NOAA Technical Memorandum NMFS 

 

 

 DECEMBER 2007

 

U.S. PACIFIC MARINE MAMMAL STOCK ASSESSMENTS: 2007 

James V. Carretta, Karin A. Forney, Mark S. Lowry, Jay Barlow, 

Jason Baker, Brad Hanson, and Marcia M. Muto 

with contributions from 

 Dale Sweetnam, Chris Yates, Dave Johnston, and Joe Cordaro 

NOAA-TM-NMFS-SWFSC-414 

 U. S. DEPARTMENT OF COMMERCE 

 National Oceanic and Atmospheric Administration 

 National Marine Fisheries Service 

 Southwest Fisheries Science Center 
i

TABLE OF CONTENTS

Draft stock assessment reports and appendices revised in 2007 are highlighted; all others are reprinted as they appear 

in the 2006 Pacific Region Stock Assessment Reports (Carretta et al. 2007). 

PINNIPEDS

CALIFORNIA SEA LION (Zalophus californianus californianus): U.S. Stock..........................................................1 

HARBOR SEAL (Phoca vitulina richardsi): California Stock.....................................................................................9 

HARBOR SEAL (Phoca vitulina richardsi): Oregon & Washington Coast Stock....................................................16 

HARBOR SEAL (Phoca vitulina richardsi): Washington Inland Waters Stock .......................................................23 

NORTHERN ELEPHANT SEAL (Mirounga angustirostris): California Breeding Stock........................................29

GUADALUPE FUR SEAL (Arctocephalus townsendi) .............................................................................................34 

NORTHERN FUR SEAL (Callorhinus ursinus): San Miguel Island Stock ...............................................................38 

HAWAIIAN MONK SEAL (Monachus schauinslandi).............................................................................................43 

CETACEANS - U.S. WEST COAST

HARBOR PORPOISE (Phocoena phocoena): Morro Bay Stock ...............................................................................51 

HARBOR PORPOISE (Phocoena phocoena): Monterey Bay Stock..........................................................................56 

HARBOR PORPOISE (Phocoena phocoena): San Francisco-Russian River Stock...................................................61

HARBOR PORPOISE (Phocoena phocoena): Northern California/Southern Oregon Stock.....................................66

HARBOR PORPOISE (Phocoena phocoena): Oregon/Washington Coast Stock .....................................................70 

HARBOR PORPOISE (Phocoena phocoena): Washington Inland Waters Stock .....................................................75

DALL'S PORPOISE (Phocoenoides dalli): California/Oregon/Washington Stock ...................................................82 

PACIFIC WHITE-SIDED DOLPHIN (Lagenorhynchus obliquidens): 

 California/Oregon/Washington, Northern and Southern Stocks ...................................................................87 

RISSO'S DOLPHIN (Grampus griseus): California/Oregon/Washington Stock .......................................................92 

BOTTLENOSE DOLPHIN (Tursiops truncatus): California Coastal Stock .............................................................97 

BOTTLENOSE DOLPHIN (Tursiops truncatus): California/Oregon/Washington Offshore Stock........................102 

STRIPED DOLPHIN (Stenella coeruleoalba): California/Oregon/Washington Stock............................................106 

SHORT-BEAKED COMMON DOLPHIN (Delphinus delphis): California/Oregon/Washington Stock................110 

LONG-BEAKED COMMON DOLPHIN (Delphinus capensis): California Stock.................................................116 

NORTHERN RIGHT-WHALE DOLPHIN (Lissodelphis borealis): California/Oregon/Washington ....................121 

KILLER WHALE (Orcinus orca): Eastern North Pacific Offshore Stock ...............................................................126

KILLER WHALE (Orcinus orca): Eastern North Pacific Southern Resident Stock ................................................131

SHORT-FINNED PILOT WHALE (Globicephala macrorhynchus): California/Oregon/Washington ..................137 

BAIRD'S BEAKED WHALE (Berardius bairdii): California/Oregon/Washington Stock .....................................142 

MESOPLODONT BEAKED WHALES (Mesoplodon spp.): California/Oregon/Washington Stocks ....................146 

CUVIER'S BEAKED WHALE (Ziphius cavirostris): California/Oregon/Washington Stock.................................151 

PYGMY SPERM WHALE (Kogia breviceps): California/Oregon/Washington Stock ...........................................155 

DWARF SPERM WHALE (Kogia sima): California/Oregon/Washington Stock....................................................159 

SPERM WHALE (Physeter macrocephalus): California/Oregon/Washington Stock .............................................163

HUMPBACK WHALE (Megaptera novaeangliae): California/Oregon/Washington Stock ....................................169 

BLUE WHALE (Balaenoptera musculus): Eastern North Pacific Stock..................................................................176 

FIN WHALE (Balaenoptera physalus): California/Oregon/Washington Stock.......................................................182

BRYDE'S WHALE (Balaenoptera edeni): Eastern Tropical Pacific Stock.............................................................187

SEI WHALE (Balaenoptera borealis): Eastern North Pacific Stock .......................................................................192 

MINKE WHALE (Balaenoptera acutorostrata): California/Oregon/Washington Stock ........................................197 
ii

CETACEANS - HAWAII

ROUGH-TOOTHED DOLPHIN (Steno bredanensis): Hawaiian Stock ..................................................................202 

RISSO'S DOLPHIN (Grampus griseus): Hawaiian Stock ........................................................................................205 

BOTTLENOSE DOLPHIN (Tursiops truncatus): Hawaiian Stock ..........................................................................209 

PANTROPICAL SPOTTED DOLPHIN (Stenella attenuata): Hawaiian Stock .......................................................214 

SPINNER DOLPHIN (Stenella longirostris): Hawaiian Stock.................................................................................219 

STRIPED DOLPHIN (Stenella coeruleoalba): Hawaiian Stock...............................................................................223 

FRASER’S DOLPHIN (Lagenodelphis hosei): Hawaiian Stock ..............................................................................226 

MELON-HEADED WHALE (Peponocephala electra): Hawaiian Stock ................................................................228 

PYGMY KILLER WHALE (Feresa attenuata): Hawaiian Stock ............................................................................231 

FALSE KILLER WHALE (Pseudorca crassidens): Pacific Islands Region Stocks (Hawaii and Palmyra Atoll)....234 

KILLER WHALE (Orcinus orca): Hawaiian Stock .................................................................................................239 

SHORT-FINNED PILOT WHALE (Globicephala macrorhynchus): Hawaiian Stock ...........................................242 

BLAINVILLE'S BEAKED WHALE (Mesoplodon densirostris): Hawaiian Stock.................................................247 

CUVIER'S BEAKED WHALE (Ziphius cavirostris): Hawaiian Stock....................................................................251 

LONGMAN’S BEAKED WHALE (Indopacetus pacificus): Hawaiian Stock .........................................................254 

PYGMY SPERM WHALE (Kogia breviceps): Hawaiian Stock ..............................................................................257 

DWARF SPERM WHALE (Kogia sima): Hawaiian Stock ......................................................................................260 

SPERM WHALE (Physeter macrocephalus): Hawaiian Stock.................................................................................263 

BLUE WHALE (Balaenoptera musculus): Western North Pacific Stock.................................................................268 

FIN WHALE (Balaenoptera physalus): Hawaiian Stock..........................................................................................272 

BRYDE'S WHALE (Balaenoptera edeni): Hawaiian Stock .....................................................................................275 

SEI WHALE (Balaenoptera borealis): Hawaiian Stock ...........................................................................................278 

MINKE WHALE (Balaenoptera acutorostrata): Hawaiian Stock ...........................................................................281 

APPENDICES

APPENDIX 1: Description of U.S. Commercial Fisheries .......................................................................................284 

APPENDIX 2: Cetacean Survey Effort.....................................................................................................................309 

APPENDIX 3: Summary of 2007 U.S. Pacific Marine Mammal Stock Assessment Reports...................................315 
iii

PREFACE 

 Under the 1994 amendments to the Marine Mammal Protection Act (MMPA), the National Marine 

Fisheries Service (NMFS) and the U.S. Fish and Wildlife Service (USFWS) are required to publish Stock 

Assessment Reports for all stocks of marine mammals within U.S. waters, to review new information every year for 

strategic stocks and every three years for non-strategic stocks, and to update the stock assessment reports when 

significant new information becomes available. This report presents revised stock assessments for 29 Pacific marine 

mammal stocks under NMFS jurisdiction, including 9 “strategic” stocks and 20 “non-strategic” stocks (see summary 

table). Information on the remaining 32 Pacific region stocks is reprinted without revision in this report and also 

appears in the 2006 reports (Carretta et al. 2007). Stock Assessments for Alaskan marine mammals are published 

by the National Marine Mammal Laboratory (NMML) in a separate report. 

 The 29 revised stock assessments in this report include those studied by the Southwest Fisheries Science 

Center (SWFSC, La Jolla, California), the Pacific Islands Fisheries Science Center (PIFSC, Honolulu, Hawaii), the 

National Marine Mammal Laboratory (NMML, Seattle, Washington), and the Northwest Fisheries Science Center in 

Seattle, WA. Northwest Fisheries Science Center staff prepared the report on the Eastern North Pacific Southern 

Resident killer whale. National Marine Mammal Laboratory staff prepared the report for the Oregon and 

Washington coast harbor seal stock. Pacific Islands Fisheries Science Center staff prepared the report on the 

Hawaiian monk seal. Southwest Fisheries Science Center staff prepared stock assessments for the remaining 26 

stocks, which include 22 U.S. west coast cetacean stocks, two stocks of false killer whales (Hawaii and Palmyra 

Atoll), the California sea lion, and northern elephant seal. 

A new stock of false killer whales (Palmyra Atoll) has been added to this year’s reports to reflect the 

availability of new genetic information for this species in the Pacific Islands Region. Both the ‘Hawaii’ and 

‘Palmyra Atoll’ false killer whale stocks are included in a single report, labeled the “Pacific Islands Region Stock 

Complex”. The intention of combining stocks into one species report is to consolidate general text about the species 

and thus reduce the number of printed pages. The status of two U.S. west coast cetacean stocks 

(‘California/Oregon/Washington short-finned pilot whales’ and ‘California long-beaked common dolphins’) has 

changed from “non-strategic” to “strategic”, based on new estimates of abundance and updates of incidental fishery 

mortality levels. The stock previously referred to as ‘East North Pacific Humpback Whale’ has undergone a name 

change to ‘California/Oregon/Washington Humpback Whale’, to reflect that the stock structure of humpback whales 

is better defined based on feeding areas rather than breeding grounds. 

 Draft versions of the stock assessment reports were reviewed by the Pacific Scientific Review Group at the 

November 2006 Seattle meeting. The authors also wish to thank those who provided unpublished data, especially 

Robin Baird and Joseph Mobley, who provided valuable information on Hawaiian cetaceans. We also thank those 

who provided input during the public comment period. Any omissions or errors are the sole responsibility of the 

authors. 

 This is a working document and individual stock assessment reports will be updated as new information on 

marine mammal stocks and fisheries becomes available. Background information and guidelines for preparing stock 

assessment reports are reviewed in Wade and Angliss (1997). The authors solicit any new information or comments 

which would improve future stock assessment reports. 

These Stock Assessment Reports summarize information from a wide range of sources and an 

extensive bibliography of all sources is given in each report. We strongly urge users of this document to refer 

to and cite original literature sources rather than citing this report or previous Stock Assessment Reports. If 

the original sources are not accessible, the citation should follow the format: [Original source], as cited in 

[this Stock Assessment Report citation]. This report should be cited as: 

Carretta, J.V., K.A. Forney, M.S. Lowry, J. Barlow, J. Baker, B. Hanson, and M.M. Muto. 2007. U.S. Pacific 

Marine Mammal Stock Assessments: 2007. US Department of Commerce, NOAA Technical 

Memorandum, NMFS-SWFSC-414. 320 p. 

Cover photograph: California sea lion (Zalophus californianus). Photo by Mark S. Lowry 
iv

References:

Carretta, J.V., K.A. Forney, M.M. Muto, J. Barlow, J. Baker, Brad Hanson, and M.S. Lowry. 2007. U.S. Pacific 

Marine Mammal Stock Assessments: 2006. U.S. Department of Commerce, NOAA Technical 

Memorandum NMFS-SWFSC-398. 312p. 

Wade, P.R. and R.P. Angliss. 1997. Guidelines for assessing marine mammal stocks: Report of the GAMMS 

workshop April 3-5, 1996, Seattle, Washington. NOAA Technical Memorandum NMFS-OPR-12. 

Available from Office of Protected Resources, National Marine Fisheries Service, Silver Spring, MD. 93p. 
Revised 10/30/2007 

CALIFORNIA SEA LION (Zalophus californianus californianus): U.S. Stock

STOCK DEFINITION AND GEOGRAPHIC RANGE 

 The California sea lion Zalophus californianus 

includes three subspecies: Z. c. wollebaeki (on the 

Galapagos Islands), Z. c. japonicus (in Japan, but now 

thought to be extinct), and Z. c. californianus (found from 

southern Mexico to southwestern Canada; herein referred 

to as the California sea lion). The breeding areas of the 

California sea lion are on islands located in southern 

California, western Baja California, and the Gulf of 

California (Figure 1). These three geographic regions are 

used to separate this subspecies into three stocks: (1) the 

United States stock begins at the U.S./Mexico border and 

extends northward into Canada; (2) the Western Baja 

California stock extends from the U.S./Mexico border to 

the southern tip of the Baja California Peninsula; and (3) 

the Gulf of California stock which includes the Gulf of 

California from the southern tip of the Baja California 

peninsula and across to the mainland and extends to 

southern Mexico (Lowry et al. 1992). Some movement 

has been documented between these geographic stocks, 

but rookeries in the United States are widely separated 

from the major rookeries of western Baja California, 

Mexico. Males from western Baja California rookeries 

may spend most of the year in the United States. Genetic 

differences have been found between the U.S. stock and 

the Gulf of California stock (Maldonado et al. 1995). There 

are no international agreements for joint management of 

California sea lions between the U.S., Mexico, and Canada. 

Figure 1. Geographic range of California 

sea lions showing stock boundaries and 

locations of major rookeries. The U.S. stock 

ranges north into Canadian waters. 

POPULATION SIZE

 The entire population cannot be counted because all age and sex classes are never ashore at the same time. 

In lieu of counting all sea lions, pups are counted during the breeding season (because this is the only age class that 

is ashore in its entirety), and the number of births is estimated from the pup count. The size of the population is then 

estimated from the number of births and the proportion of pups in the population. 

 Censuses are conducted in July after all pups have been born. To estimate the number of pups born, the 

pup count in 2005 (48,277) was adjusted for an estimated 15% pre-census mortality (Boveng 1988; Lowry et al. 

1992), giving an estimated 55,519 live births in the population. The fraction of newborn pups in the population 

(23.3%) was estimated from a life table derived for the northern fur seal (Callorhinus ursinus) (Boveng 1988, Lowry 

et al. 1992) which was modified to account for the growth rate of this California sea lion population (5.6% yr-1, see 

below). Multiplying the number of pups born by the inverse of this fraction (4.28) results in a population estimate 

of 238,000. 

Minimum Population Estimate

 The minimum population size was determined from counts of all age and sex classes that were ashore at all 

the major rookeries and haulout sites during the 2005 breeding season. The minimum population size of the U.S. 

stock is 141,842 (NMFS unpubl. data). It includes all California sea lions counted during the July 2005 census at 

the Channel Islands in southern California and at haulout sites located between Point Conception and the 

Oregon/California border. An additional unknown number of California sea lions are at sea or hauled out at 

locations that were not censused.

1
Current Population Trend

 Records of pup counts from 1975 to 2005 (Figure 2) were compiled from the literature, NMFS reports, 

unpublished NMFS data, and Lowry 1999 (the literature up to 2000 is listed in Lowry and Maravilla 2005). Pup 

counts from 1975 through 2005 were examined for four rookeries in southern California and for haulouts in central 

and northern California. The number of pups at rookeries not counted were estimated using multiple regressions 

derived from counts of two neighboring rookeries using data from 1975-2000 (Lowry and Maravilla 2005) : (1) 

1980 at Santa Barbara Is.; (2) 1978-1980 at San Clemente Is.; and (3) 1978 and 1979 at San Nicolas Is. The mean 

was used when more than one count was available for a given rookery. Four major declines in the number of pups 

counted occurred during El Niño events in 1983-1984, 1992-93, 1998, and 2003 (Figure 2). A regression of the 

natural logarithm of the pup counts against year indicates that the counts of pups increased at an annual rate of 5.6% 

between 1975 and 2005 when pup counts for El Niño years (1983, 1984, 1992, 1993, 1998, and 2003) were removed 

from the 1975-2005 time series. 

CALIFORNIA SEA LION PUPS

United States 

0

10,000

20,000

30,000

40,000

50,000

60,000

1970 1975 1980 1985 1990 1995 2000 2005 2010

YEAR

COUNT

Counts

Counts and estimates

 The 1975-2005 time series of pup counts shows the effect of four El Niño events on the sea lion population. 

Pup production decreased by 35 percent in 1983, 27 percent in 1992, and 64 percent in 1998. After the 1992-93 and 

1997-98 El Niños, pup production rebounded by 52 percent and 185 percent, respectively, but there was no rebound 

after the 1983-84 El Niño (Figure 2). Unlike the 

1992-93 and 1997-98 El Niños, the 1983-1984 El 

Niño affected adult female survivorship (DeLong 

et al 1991) which prevented the rebound in pup 

production because there were fewer adult females 

available in the population to produce pups (it took 

five years for pup production to return to the 1982 

level). Other characteristics of El Niños are higher 

pup and juvenile mortality rates (DeLong et al 

1991, NMFS unpubl. data) which affect future 

recruitment into the adult population for the 

affected cohorts. The 2002 and 2003 decline can 

be attributed to (1) reduced number of reproductive 

adult females being incorporated into the 

population as a result of the 1992-93 and 1997-98 

El Niños, (2) domoic acid poisoning (Scholin et al. 

2000, Lefebvre et al. 2000), (3) lower survivorship 

of pups due to hookworm infestations (Lyons et al. 

2001), and (4) the 2003 El Niño 

Figure 2. U.S. pup count index for California sea lions 

(1975-2005).

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 A generalized logistic growth model indicated that the maximum population growth rate (Rmax) was 6.52 

percent when pup counts from El Niño years (1983, 1984, 1992, 1993, 1998, and 2003) were removed (Figure 3). 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size 

(141,842) times one half the default maximum net growth rate for pinnipeds (1⁄2 of 12%) times a recovery factor of 

1.0 (for a stock of unknown status that is growing, Wade and Angliss 1997); resulting in a PBR of 8,511 sea lions 

per year. 

ANNUAL HUMAN-CAUSED MORTALITY

Historical Depletion 

Historic exploitation of California sea lions include harvest for food by native Californians in the Channel 

Islands 4,000-5,000 years ago (Stewart et al. 1993) and for oil and hides in the mid-1800s (Scammon 1874). More 

recent exploitation of sea lions for pet food, target practice, bounty, trimmings, hides, reduction of fishery 

depredation, and sport are reviewed in Helling (1984), Cass (1985), Seagers et al. (1985), and Howorth (1993). 

Lowry et al. (1992) stated that there were few historical records to document the effects of such exploitation on sea 

lion abundance. 

2
Fisheries Information

 California sea lions are killed incidentally in set and drift gillnet fisheries (Hanan et al. 1993; Barlow et al. 

1994; Julian 1997; Julian and Beeson, 1998, Cameron and Forney 1999; Carretta et al. 2005a; Table 1). Detailed 

information on these fisheries is provided in Appendix 1. Mortality estimates for the California the set and drift 

gillnet fisheries are included in Table 1 for the five most recent years of monitoring, 2000-2004 (Carretta and 

Chivers 2004, Carretta et al. 2005a, 2005b). A controlled experiment during 1996-97 demonstrated that the use of 

acoustic warning devices (pingers) reduced sea lion entanglement rates considerably within the drift gillnet fishery 

(Barlow and Cameron 2003). However, entanglement rates increased again during the 1997 El Niño and continued 

during 1998. The reasons for the increase in entanglement rates are unknown. However, it has been suggested that 

sea lions may have foraged further offshore in response to limited food supplies near rookeries, which would 

provide opportunity for increased interactions with the drift gillnet fishery. Because of interannual variability in 

entanglement rates, additional years of data will be required to fully evaluate the effectiveness of pingers for 

reducing mortality of this particular species. Mortality estimates from the drift gillnet fishery are based on 2000-

2004 observer data (~20% observer coverage). In past years, the largest source of sea lion mortality has been in the 

California halibut and angel shark set gillnet fishery, which currently operates south of Point Arguello, California 

and has not been observed throughout its range since 1994. Limited observer coverage occurred in Monterey Bay in 

2000 and 2001, but represented less than 5% of the total fishing effort. Given the lack of recent observer data, it is 

not possible to estimate sea lion mortality for this fishery. Evidence from fisher self-reports (Table 1) indicates that 

mortality of sea lions still occurs in this fishery, but it is not possible to extrapolate these self reports to overall 

mortality because these self reports have been shown to be grossly underreported. Logbook and observer data, and 

fisher reports, indicate that mortality of California sea lions occurs, or has occurred in the past in the following 

fisheries: (1) California, Oregon, and Washington salmon troll fisheries; (2) Oregon and Washington non-salmon 

troll fisheries; (3) California herring purse seine fishery; (4) California anchovy, mackerel, and tuna purse seine 

fishery; (5) California squid purse seine fishery, (6) Washington, Oregon, California and British Columbia, Canada 

salmon net pen fishery, (7) Washington, Oregon, California groundfish trawl fishery, (8) Washington, Oregon and 

California commercial passenger fishing vessel fishery (NMFS 1995, M. Perez pers. comm, and P. Olesiuk pers. 

comm.) (9) the California small mesh drift gillnet fishery, and (10) the California purse seine fishery for anchovy, 

mackerel, and tuna. The OR Columbia River gillnet fishery has been reduced to such levels that California sea lion 

mortality, if any, is negligible (J. Scordino, per. comm.). Stranding data from California, Oregon, and Washington 

during 2000-2004 shows that an additional 66 sea lions died from unknown entangling net fisheries (Table 1). 

Animals are typically found on the beach or sometimes at sea with portions of gillnet wrapped around the carcass. 

This represents a minimum number of animals killed, as many entanglements are likely unreported or undetected. 

 Drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of Baja California, 

Mexico and may take animals from 

the same population. Quantitative 

data are available only for the 

Mexican swordfish drift gillnet 

fishery, which uses vessels, gear, and 

operational procedures similar to 

those in the U.S. drift gillnet fishery, 

although nets may be up to 4.5 km 

long (Holts and Sosa-Nishizaki 

1998). The fleet increased from two 

vessels in 1986 to 31 vessels in 1993 

(Holts and Sosa-Nishizaki 1998). 

The total number of sets in this 

fishery in 1992 can be estimated from 

data provided by these authors to be 

approximately 2700, with an 

observed rate of marine mammal 

bycatch of 0.13 animals per set (10 

marine mammals in 77 observed sets; 

Sosa-Nishizaki et al. 1993). This 

overall mortality rate is similar to that 

observed in California driftnet 

fisheries during 1990-95 (0.14 marine 

1975 1980 1985 1990 1995 2000 2005

0 10000 20000 30000 40000 50000

Year

Abundance

1997

K = 4.6824e+04

MNPL = 3.9801e+04

Figure 3. Generalized logistic growth of California sea lion pup 

counts obtained during 1975-2005 (excluding El Niño years) 

indicating when Maximun Net Productivity Level (MNPL) was 

reached and that the population has reached carrying capacity (K). 

3
mammals per set; Julian and Beeson, 1998), but species-specific information is not available for the Mexican 

fisheries. Previous efforts to convert the Mexican swordfish driftnet fishery to a longline fishery have resulted in a 

mixed fishery, with 20 vessels alternately using longlines or driftnets, 23 using driftnets only, 22 using longlines 

only, and seven with unknown gear type (Berdegué 2002). 

Table 1. Summary of available information on the mortality and serious injury of California sea lions in commercial 

fisheries that might take this species (Carretta 2001; 2002, Carretta et al. 2005a, 2005b, Perez 2003, Perez 2003; 

Appendix 1). Mean annual takes are based on 2000-2004 data unless noted otherwise. In past years, the set gillnet 

fishery for halibut and angel shark has been responsible for the majority of fishery-related mortalities. However, 

this fishery has not been observed recently and thus, current estimates of mortality are unknown. Because current 

mortality estimates are lacking for this fishery, overall mean annual takes reported in Table 1 are negatively biased 

by an unknown amount. 

Fishery Name Year(s) Data Type

Percent Observer 

Coverage

Observed

Mortality

Estimated 

Mortality (CV in 

parentheses)

Mean 

Annual Takes 

(CV in parentheses)

CA/OR thresher 

shark/swordfish large 

mesh drift gillnet fishery 

2000 

2001 

2002 

2003 

2004 

observer 

22.9% 

20.4% 

22.1% 

20.2% 

20.6% 

13 

2 

18 

4 

6 

50 (0.43) 

10 (0.67) 

81 (0.25) 

20 (0.50) 

29 (0.44) 

38 (0.18) 

CA angel shark/halibut 

and other species large 

mesh (>3.5 in) set gillnet 

fishery 

2001 

2002 

2003 

2004 

2005 

2000-2004 

No fisherywide observer 

program since 

1994 

MMAP self 

reports 

0% 

0% 

0% 

0% 

0% 

- 

n/a 

n/a 

n/a 

n/a 

n/a 

57 

n/a 

n/a 

n/a 

n/a 

n/a 

n/a 

n/a 

≥11.4 

CA small-mesh drift 

gillnet fishery for white 

seabass, yellowtail, 

barracuda, and tuna 

20031

20041 observer 11%1 11%1

2 

1 

18 (0.71) 

9 (0.94) 13.5 (0.57) 

CA anchovy, mackerel, 

and tuna purse seine 

fishery 

20042 observer n/a 1 ≥ 1 (n/a) ≥ 1 (n/a) 

WA, OR, CA domestic 

groundfish trawl fishery 

(At-sea processing Pacific 

whiting fishery only)

2000 

2001 

2002 

2003 

2004 

observer 

80.6% 

96.2% 

100% 

100% 

100% 

0 

0 

1 

2 

2 

0 

0 

1 

2 

2 

1.2 (0) 

WA, OR, CA domestic 

groundfish trawl fishery 

(bottom trawl) 

2000 

2001 

2002 

2003 

2004 

observer n/a 

n/a 

8 

6 

24 

6 

n/a ≥11 

WA, OR salmon net pen 

fishery

2000 

2001 

2002 

2003 

2004

n/a n/a n/a n/a n/a

Canada: BC salmon pen 

fishery

2000 

2001 

2002 

2003 

2004 

MMAP n/a 

225 

88 

19 

14 

6 

225 

88 

19 

14 

6 

≥70 

4
Fishery Name Year(s) Data Type

Percent Observer 

Coverage

Observed 

Mortality

Estimated 

Mortality (CV in 

parentheses)

Mean 

Annual Takes 

(CV in parentheses)

Unknown entangling net 

fishery 2000-2004 stranding n/a 66 n/a 13 (n/a) 

Minimum total annual takes ≥159 (n/a) 

1 A pilot observer program existed for two years in the small mesh drift gillnet fishery, where observer coverage ranged between 11-17%, based 

on logbook effort data and 22 observed sets in 2003 and 2004, respectively. 

Other Mortality 

 California sea lions injured by entanglement in gillnet and other man-made debris have been observed at 

rookeries and haulouts (Stewart and Yochem 1987, Oliver 1991). The proportion of those entangled ranged from 

0.08% to 0.35% of those hauled out, with the majority (52%) entangled in monofilament gillnet. Data from a marine 

mammal rehabilitation center showed that 87% of 87 rescued California sea lions were entangled in 4-4.5 inch 

square-mesh monofilament gillnet (Howorth 1994). Of California sea lions entangled in gillnets, 0.8% in set gillnets 

and 5.4% in drift gillnets were observed to be released alive from the net by fishers during 1991-1995 (Julian and 

Beeson 1998). Clearly, some are escaping from gillnets; however, the rate of escape from gillnets, as well as the 

mortality rate of these injured animals, is unknown. 

 Live strandings and dead beach-cast California sea lions are regularly observed with gunshot wounds in 

California (Lowry and Folk 1987, Deiter 1991, Barocchi et al. 1993, Goldstein et al. 1999, NMFS unpublished 

stranding data). A summary of records for 2000-2004 from the California Marine Mammal Stranding Network 

(CMMSN) and the Oregon and Washington stranding databases shows the following non-fishery related mortalities: 

boat collisions (17 mortalities), entrainment in power plants (106 mortalities), shootings (237 mortalities), marine 

debris (three mortalities), and unknown sources (seven mortalities). Stranding records are a gross under-estimate of 

injury and mortality because many animals and carcasses are never recorded. There are currently no estimates of 

the total number of California sea lions being killed or injured by guns, boat collisions, entrainment in power plants, 

marine debris, or gaffs, but the minimum number from 2000-2004 was 370. The average annual non-fishery related 

mortality of sea lions from 2000-2004 is a minimum of the 370 mortalities listed above, divided by 5 years = 74 sea 

lions annually. 

 Several Pacific Northwest treaty Indian tribes have promulgated tribal regulations allowing tribal 

members to exercise treaty rights for subsistence harvest of sea lions. Current estimates of annual take are zero to 

two animals per year. 

 Sea lion mortalities in 1998 along the central California coast have recently been linked to the algalproduced neurotoxin domoic acid (Scholin et al. 2000). Future mortalities may be expected to occur, due to the 

periodic nature of such harmful algal blooms. 

STATUS OF STOCK

 A generalized logistic growth model of pup counts obtained during 1975-2005 (excluding El Niño years) 

indicated that the population reached its Maximum Net Productivity Level (MNPL) of 39,800 pups in 1997 and has 

reached carrying capacity (K) at 46,800 pups per year (z = 19.09, Rmax = 0.0652, n0 = 10,100, SE = 1,055) (Figure 

3). This determination should be taken with caution until more years of data have been collected to verify whether 

the flattening of the generalized logistic curve persists in future years. California sea lions in the U.S. are not listed 

as "endangered" or "threatened" under the Endangered Species Act or as "depleted" under the MMPA. Even 

though current total human-caused mortality is unknown (due a lack of observer coverage in the California set 

gillnet fishery that historically has been the largest source of human-caused mortalities), California sea lions are not 

considered a "strategic" stock under the MMPA because (based on historical takes in the set gillnet fishery and 

current levels of fishing effort) total human-caused mortality is still likely to be less than the PBR (8,511). The total 

fishery mortality and serious injury rate for this stock likely remains above 10% of the calculated PBR and, 

therefore, cannot be considered to be insignificant and approaching a zero mortality and serious injury rate. 

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5
Barlow, J. and G. A. Cameron. 2003. Field experiments show that acoustic pingers reduce marine mammal bycatch 

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Marine Mammals, Galveston TX, November 11-15, 1993. 

Berdegué, J. 2002. Depredación de las especies pelágicas reservadas a la pesca deportiva y especies en peligro de 

extinción con uso indiscriminado de artes de pesca no selectivas (palangres, FAD's, trampas para peces y 

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picudos. A.C. Mazatlán, Sinaloa, 21 de septiembre. 

Boveng, P. 1988. Status of the California sea lion population on the U.S. west coast. Admin. Rep. LJ-88-07. 

Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La Jolla, CA 92038. 

26 pp. 

Brown, R. F. and S. J. Jeffries. 1993. Preliminary report on estimated marine mammal mortality in Columbia River 

fall and winter salmon gillnet fisheries, 1991-1992. Columbia River Area Marine Mammal Observer 

Program, 53 Portway St., Astoria, OR. 13 pp. 

Carretta, J.V. and S.J. Chivers. 2004. Preliminary estimates of marine mammal mortality and biological sampling 

of cetaceans in California gillnet fisheries for 2003. Paper SC/56/SM1 presented to the IWC Scientific 

Committee, June 2004 (unpublished). [Available from Southwest Fisheries Science Center, National 

Marine Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 92037, USA]. 

Carretta, J.V., S.J. Chivers, and K. Danil. 2005a. Preliminary estimates of marine mammal bycatch, mortality, and 

biological sampling of cetaceans in California gillnet fisheries for 2004. Administrative Report LJ-05-10, 

available from Southwest Fisheries Science Center, 8604 La Jolla Shores Drive, La Jolla, California, 

92037. 17 p. 

Carretta, J.V., T. Price, D. Petersen, and R. Read. 2005b. Estimates of marine mammal, sea turtle, and seabird 

mortality in the California drift gillnet fishery for swordfish and thresher shark, 1996-2002. Marine 

Fisheries Review 66(2):21-30. 

Cass, V.L. 1985. Exploitation of California sea lions, Zalophus californianus, prior to 1972. Marine Fisheries 

Review 47:36-38. 

Deiter, R. L. 1991. Recovery and necropsy of marine mammal carcasses in and near the Point Reyes National 

Seashore, May 1982-March 1987. In J. E. Reynolds III and D. K. Odell (editors), Marine mammal 

strandings in the United States, Proceedings of the second marine mammal stranding workshop, Miami, 

Florida, December 3-5-1987. p. 123-141. NOAA Technical Rept. NMFS 98. 

Goldstein, T., S. P. Johnson, A. V. Phillips, K. D. Hanni, D. A. Fauquier, and F. M. D. Gulland. 1999. Aquatic 

Mammals 25:43-51. 

DeLong, R. L., G. A. Antonelis, C. W. Oliver, B. S. Stewart, M. S. Lowry, and P. K. Yochem. 1991. Effects of the 

1982-1983 El Niño on several population parameters and diet of California sea lions on the California 

Channel Islands. In F. Trillmich and K. A. Ono (editors), Pinnipeds and El Niño: Responses to 

environmental stress. p. 166-172. Springer-Verlag, Berlin Heidelberg New York. 

Hanan, D. A., and S. L. Diamond. 1989. Estimates of sea lion, harbor seal, and harbor porpoise mortalities in 

California set net fisheries for the 1986-87 fishing year. Final Report. Cooperative agreement No. NA-86-

ABH-00018. NOAA/NMFS SWR, January 1989. 10 pp. 

Hanan, D. A., D. B. Holts, and A. L. Coan, Jr. 1993. The California drift gill net fishery for sharks and swordfish, 

1981-82 through 1990-91. Calif. Dept. Fish and Game Fish. Bull. No. 175. 95 p. 

Hanan, D. A., J. P. Scholl, and S. L. Diamond. 1988. Estimates of sea lion and harbor seal mortalities in California 

set net fisheries for 1983, 1984, and 1985. Final Report. Cooperative agreement No. NA-86-ABH-00018. 

NOAA/NMFS SWR October 1988. 10 pp. 

Helling, H.E. 1984. A follow-up report on available data for California and Stellar sea lion (Zalophus 

californianus), Eumetopias jubata) exploitation prior to 1950. Administrative Report LJ-84-45C. National 

Marine Fisheries Service, Southwest Fisheries Center, La Jolla, CA 92037. 10pp. 

Holts, D. and O. Sosa-Nishizaki. 1998. Swordfish, Xiphias gladius, fisheries of the eastern North Pacific Ocean. In: 

I. Barrett, O. Sosa-Nishizaki and N. Bartoo (eds.). Biology and fisheries of swordfish, Xiphias gladius. 

Papers from the International Symposium on Pacific Swordfish, Ensenada Mexico, 11-14 December 1994. 

U.S. Dep. Commer., NOAA Tech. Rep. NMFS 142, 276 pp. 

Howorth, P.C. 1993. Commercial collection of pinnipeds in the California Channel Islands, 1877-1981. In:

Hochberg, F. G. (editor), Third California Islands Symposium: Recent Advances in Research in the 

California Islands. Santa Barbara, CA, Santa Barbara Museum of Natural History. pp. 

6
Howorth, P. C. 1994. Entanglement of marine mammals in synthetic debris. In W. L. Halvorson and G. J. Maender 

(editors), The Fourth California Islands Symposium: Update on the status of resources, p. 111-121. 

Julian, F. 1997. Cetacean mortality in California gill net fisheries: Preliminary estimates for 1996. Paper 

SC/49/SM02 presented to the International Whaling Commission, September 1997 (unpublished). 13 pp. 

Julian, F. And M. Beeson. 1998. Estimates for marine mammal, turtle, and seabird mortality for two California 

gillnet fisheries: 1990-1995. Fish. Bull. 96:271-284. 

Lefebvre, K. C. Powell, G. Doucette, J. Silver, P. Miller, P. Hughes, M. Silver, and R. Tjeerdemma. 2000. Domoic 

acid-producing diatoms: probable cause of neuroexcitotoxicity in California sea lions. Marine 

Environmental Research 50:485-488. 

Lowry, M. S. 1999. Counts of California sea lion (Zalophus californianus) pups from aerial color photographs and 

 from the ground: a comparison of two methods. Marine Mammal Science 15:143-158. 

Lowry, M. S. and R. L. Folk. 1987. Feeding habits of California sea lions from stranded carcasses collected at San 

Diego County and Santa Catalina Island, California. Admin. Rep. LJ-87-15. Southwest Fisheries Science 

Center, National Marine Fisheries Service, P.O. Box 271, La Jolla, CA 92038. 33 pp. 

Lowry, M. S., P. Boveng, R. J. DeLong, C. W. Oliver, B. S. Stewart, H. DeAnda, and J. Barlow. 1992. Status of 

the California sea lion (Zalophus californianus californianus) population in 1992. Admin. Rep. LJ-92-32. 

Southwest Fisheries Science Center, National Marine Fisheries Service, La Jolla, CA 92038. 34 pp. 

Lowry, M. S. and O. Maravilla-Chavez. 2005. Recent abundance of California sea lions in western Baja California, 

Mexico and the United States. In D. K. Garcelon and C. A. Schwemm (editors), Proceedings of the Sixth 

California Islands Symposium, Ventura, California, December 1-3, 2003. p. 485-497. National Park 

Service Technical Publication CHIS-05-01, Institute for Wildlife Studies, Arcata, California. 

Lyons, E. T., S. R. Melin, R. L. DeLong, A. J. Orr, F. M. Gulland, and S.C. Tolliver. 2001. Current prevalence of 

adult Uncinaria spp. in northern fur seal (Callorhinus ursinus) and California sea lion (Zalophus 

californianus) pups on San Miguel Island, California, with notes on the biology of hookworms. Veterinary 

Parasitology 97:309-318. 

Maldonado, J. E., F. O. Davila, B. S. Stewart, E. Greffen, and R. K Wayne. 1995. Intraspecific genetic 

differentiation in California sea lions (Zalophus californianus) from southern California and the Gulf of 

California. Mar. Mamm. Sci. 11(1):46-58. 

Miller, D. J., M. J. Herder, and J. P. Scholl. 1983. California marine mammal-fishery interaction study, 1979-1981. 

Administrative Rept. LJ-83-13C. Southwest Fisheries Science Center, National Marine Fisheries Service, 

P.O. Box 271, La Jolla, CA. 233 p. 

NMFS. 1995. Environmental assessment of proposed regulations to govern interactions between marine mammals 

and commercial fishing operations, under Section 118 of the Marine Mammal Protection Act. Department 

of Commerce, National Oceanic and Atmospheric Administration, National Marine Fisheries Service, 

Office of Protected Resources, June 1995. 139 pp. + 4 Appendices. 

Oliver, C. W. 1991. 1988-1991 field studies on pinnipeds at San Clemente Island. Admin. Rep. LJ-91-27. 

Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La Jolla, CA 92038. 

33 pp. 

Perez, M. 2003. Compilation of marine mammal incidental take data from the domestic and joint venture 

groundfish fisheries in the U.S. EEZ of the North Pacific, 1989-2001. U.S. Dep. Commer., NOAA Tech. 

Memo. NMFS-AFSC-138. 145 pp. 

Scammon, C.M. 1874. The marine mammals of the north-western coast of North America, described and 

illustrated: Together with an account of the American whale fishery. John H. Carmany and Company, San 

Francisco, CA. 319p. 

Scholin, C. A., Gulland, F., Doucette, G. J., Benson, S., Busman, M., Chavez, F. P., Cordaro, J., DeLong, R., De 

Vogelaere, A., Harvey, J., Haulena, M., Lefebvre, K., Lipscomb, T., Loscutoff, S., Lowenstine, L. J., Marin 

III, R., Miller, P. E., McLellan, W. A., Moeller, P. D. R., Powell, C. L., Rowles, T., Silvagni, P., Silver, M., 

Spraker, T., Trainer, V., and Van Dolah, F. M. 2000. Mortality of sea lions along the central California 

coast linked to a toxic diatom bloom. Nature, 403:80-84. 

Seagers, D.J., D.P. DeMaster, and R.L. DeLong. 1985. A survey of historic rookery sites for California and 

northern sea lions in the Southern California Bight. Administrative Report LJ-85-13, National Marine 

Fisheries Service, Southwest Fisheries Center, 8604 La Jolla Shores Dr., La Jolla, CA. 

Stewart, B. S. and P. K. Yochem. 1987. Entanglement of pinnipeds in synthetic debris and fishing net and line 

fragments at San Nicolas and San Miguel Islands, California, 1978-1986. Marine Pollution Bulletin 

18:336-339. 

7
Stewart, B.S., P.K.Yochem, R.L. DeLong, and G.A. Antonelis. 1993. Trends in Abundance and Status of Pinnipeds 

on the Southern California Channel Islands. In: Hochberg, F. G. (editor), Third California Islands 

Symposium: Recent Advances in Research in the California Islands. Santa Barbara, CA, Santa Barbara 

Museum of Natural History. pp 501_516. 

8
Revised 11/01/2005 

HARBOR SEAL (Phoca vitulina richardsi): California Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

 Harbor seals (Phoca vitulina) are widely

distributed in the North Atlantic and North Pacific. 

Two subspecies exist in the Pacific: P. v. stejnegeri in 

the western North Pacific, near Japan, and P. v.

richardsi in the eastern North Pacific. The latter

subspecies inhabits near-shore coastal and estuarine 

areas from Baja California, Mexico, to the Pribilof 

Islands in Alaska. These seals do not make extensive 

pelagic migrations, but do travel 300-500 km on 

occasion to find food or suitable breeding areas (Herder 

1986; D. Hanan unpublished data). In California, 

approximately 400-600 harbor seal haulout sites are 

widely distributed along the mainland and on offshore

islands, including intertidal sandbars, rocky shores and

beaches (Hanan 1996; Lowry et al. 2005). 

 Within the subspecies P. v. richardsi, 

abundant evidence of geographic structure comes from 

differences in mitochondrial DNA (Huber et al. 1994;

Burg 1996; Lamont et al. 1996; Westlake and O’CorryCrowe 2002; O’Corry-Crowe et al. 2003), mean

pupping dates (Temte 1986), pollutant loads

(Calambokidis et al. 1985), pelage coloration (Kelly

1981) and movement patterns (Jeffries 1985; Brown 

1988). LaMont (1996) identified four discrete 

subpopulation differences in mtDNA between harbor

seals from Washington (two locations), Oregon, and 

California. Another mtDNA study (Burg 1996)

supported the existence of three separate groups of 

harbor seals between Vancouver Island and

southeastern Alaska. Although we know that

geographic structure exists along an almost continuous

distribution of harbor seals from California to Alaska, stock boundaries are difficult to draw because any 

rigid line is (to a greater or lesser extent) arbitrary from a biological perspective. Nonetheless, failure to 

recognize geographic structure by defining management stocks can lead to depletion of local populations.

Previous assessments of the status of harbor seals have recognized three stocks along the west coast of the 

continental U.S.: 1) California, 2) Oregon and Washington outer coast waters, and 3) inland waters of

Washington. Although the need for stock boundaries for management is real and is supported by biological

information, the exact placement of a boundary between California and Oregon was largely a 

political/jurisdictional convenience. An unknown number of harbor seals also occur along the west coast

of Baja California, at least as far south as Isla Asuncion, which is about 100 miles south of Punta Eugenia.

Animals along Baja California are not considered to be a part of the California stock because it is not 

known if there is any demographically significant movement of harbor seals between California and

Mexico and there is no international agreement for joint management of harbor seals. Lacking any new

information on which to base a revised boundary, the harbor seals of California will be again treated as a 

separate stock in this report (Fig. 1). Other Marine Mammal Protection Act (MMPA) stock assessment 

reports cover the five other stocks that are recognized along the U.S. west coast: Oregon/Washington outer 

coastal waters, Washington inland waters, and three stocks in Alaska coastal and inland waters. 

W132 W129 W126 W123 W120 W117

N30

N34

N38

N42

N46

WASHINGTON

OREGON

CALIFORNIA

OR/WA

COASTAL

STOCK

 CA

STOCK

PACIFIC

 OCEAN

Figure 1. Stock boundaries for the California 

and Oregon/Washington coastal stocks of

harbor seals. Dashed line represents the U.S. 

EEZ.

POPULATION SIZE

A complete count of all harbor seals in California is impossible because some are always away

from the haulout sites. A complete pup count (as is done for other pinnipeds in California) is also not

possible because harbor seals are precocious, with pups entering the water almost immediately after birth. 

9
Population size is estimated by counting the number of seals ashore during the peak haul-out period (May 

to July) and by multiplying this count by the inverse of the estimated fraction of seals on land. Boveng 

(1988) reviewed studies estimating the proportion of seals hauled out to those in the water and suggested

that a correction factor for harbor seals is likely to be between 1.4 and 2.0. Huber (1995) estimated a mean 

correction factor of 1.53 (CV=0.065) for harbor seals in Oregon and Washington during the peak pupping 

season. Hanan (1996) estimated that 83.3% (CV=0.17) of harbor seals haul out at some time during the

day during the May/June molt, and he estimated a correction factor of 1.20 based on those data. Neither

correction factor is directly applicable to an aerial photographic count in California: the 1.53 factor was 

measured at the wrong time of year (when fewer seals are hauled out) and in a different area and the 1.20

factor was based on the fraction of seals hauled out over an entire 24-hour day (correction factors for aerial 

counts should be based on the fraction of seals hauled out at the time of the survey). Hanan (pers. comm.)

revised his haul-out correction factor to 1.3 by using only those seals hauled out between 0800 and 1700

hrs which better corresponds to the timing of his surveys. Based on the most recent harbor seal counts

(26,333 in May-July 2004; Lowry et al. 2005) and Hanan’s revised correction factor, the harbor seal

population in California is estimated to number 34,233. 

Minimum Population Estimate

Because of the way it was

calculated (based on the fraction of 

seals hauled out at any time during 

a 24 hr day), Hanan’s (1996) 

correction factor of 1.2 can be

viewed as a minimum estimate of 

the fraction hauled out at a given 

instant. A population size

estimated using this correction

factor provides a reasonable 

assurance that the true population is 

greater than or equal to that

number, and thus fulfills the 

requirement of a minimum 

population estimate. The minimum 

size of the California harbor seal

population is therefore 31,600. 

Figure 2. Harbor seal haulout counts in California during

Figure 2. Harbor seal haulout counts in California during

May/June (Hanan 1996; R. Read, CDFG unpubl. data; 

NMFS unpubl. data from 2002 and 2004 surveys).

0

5,000

10,000

15,000

20,000

25,000

30,000

Number Seals Counted

1955 1965 1975 1985 1995 2005

Year

TOTAL

Mainland

Channel Islands

Current Population Trend

Counts of harbor seals in 

California showed a rapid increase from approximately 1972 (when the MMPA was first passed) to 1990

(Fig. 2). Net production rates appeared to be decreasing from 1982 to 1994 (Fig. 3). Although earlier 

analyses were equivocal (Hanan 1996) and there has been no formal determination that the California stock

has reached OSP (Optimal Sustainable Population level as defined by the MMPA), the decrease in 

population growth rate has occurred at the same time as a decrease in human-caused mortality and may

indicate that the population is approaching its environmental carrying capacity. Population growth has also 

slowed or stopped for the harbor seal stock on the outer coasts of Oregon and Washington (see separate

Stock Assessment Report). 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES 

A realized rate of increase was calculated for the 1982-1995 period (when annual counts were 

available) by linear regression of the natural logarithm of total count versus year. The slope of this

regression line was 0.035 (s.e.=0.007) which gives an annualized growth rate estimate of 3.5%. The 

current rate of net production is greater than this observed growth rate because fishery mortality takes a

fraction of the net production. Annual gillnet mortality may have been as high as 5-10% of the California 

harbor seal population in the mid-1980s; a kill this large would have depressed population growth rates 

appreciably. Net productivity was therefore calculated for 1980-1994 as the realized rate of population 

growth (increase in seal counts from year i to year i+1, divided by the seal count in year i) plus the humancaused mortality rate (fishery mortality in year i divided by population size in year i). Between 1983 and 

10
1994, the net productivity rate for the 

California stock averaged 9.2% (Fig. 3).

A regression shows a decrease in net

production rates, but the decline is not

statistically significant. Maximum net

productivity rates cannot be estimated

because measurements were not made 

when the stock size was very small. 

-0.2

-0.1

0

0.1

0.2

0.3

0.4

Net Production Rate

1982 1984 1986 1988 1990 1992 1994

Year

Harbor Seal Net Production in CA

POTENTIAL BIOLOGICAL 

REMOVAL

The potential biological removal

(PBR) level for this stock is calculated as 

the minimum population size ( 31,600) 

times one half the default maximum net

productivity rate for pinnipeds (1⁄2 of

12%) times a recovery factor of 1.0 (for a

stock of unknown status that is growing

or for a stock at OSP, Wade and Angliss 

1997), resulting in a PBR of 1,896.

Figure 3. Net production rates and regression line 

estimated from haulout counts and fishery mortality. HUMAN-CAUSED MORTALITY 

AND SERIOUS INJURY

Historical Takes 

Prior to state and federal protection and especially during the nineteenth century, harbor seals

along the west coast of North America were greatly reduced by commercial hunting (Bonnot 1928, 1951;

Bartholomew and Boolootian 1960). Only a few hundred individuals survived in a few isolated areas along 

the California coast (Bonnot 1928). In the last half of this century, the population has increased 

dramatically. 

Fishery Information

A summary of known fishery mortality and injury for this stock of harbor seals is given in Table 1. 

More detailed information on these fisheries is provided in Appendix 1. Because the vast majority of

harbor seal mortality in California fisheries occurs in the set gillnet fishery, because that fishery has 

undergone dramatic reductions and redistributions of effort, and because the entire fishery has not been

observed since 1994, average annual mortality cannot be accurately estimated for the recent years (1999-

2003). Rough estimates for 1999-2003 have been made by extrapolation of prior kill rates using recent 

effort estimates and observations in the Monterey portion of the fishery from 1999 and 2000 (Table 1).

Observations from the Monterey Bay portion of the fishery included 57 and 24 harbor seals taken in 1999

and 2000, respectively. Stranding data reported to the California Marine Mammal Stranding Network from

1999-2003 include harbor seal deaths and injuries caused by hook-and-line fisheries (four deaths, two

injuries) and gillnet fisheries (two deaths, two injuries). The locations and timing of harbor seal strandings

attributed to gillnet fisheries suggest that the halibut/angel shark or white seabass set gillnet fishery are 

responsible for the interactions (see Appendix 1 for fishery descriptions). 

Other Mortality

The California Marine Mammal Stranding database maintained by the National Marine Fisheries

Service, Southwest Region, contains the following records of human-related harbor seal mortalities and 

injuries in 1999-2003: (1) boat collision ( eight mortalities, two injuries), (2) entrainment in power plants 

(26 mortalities), (3) shootings ( 15 mortalities), and (4) all-terrain vehicle (ATV) collision (one injury). 

11
Table 1. Summary of available information on the mortality and serious injury of harbor seals (California 

stock) in commercial fisheries that might take this species (Cameron and Forney 2000; Carretta 2001,

2002; Carretta et al. 2003; Carretta and Chivers 2004). n/a indicates that data are not available. Mean 

annual takes are based on 1999-2003 data unless noted otherwise. 

Fishery Name Year(s) Data Type

Percent 

Observer 

Coverage

Observed

Mortality

Estimated 

Mortality (CV in

parentheses)

Mean 

Annual Takes 

(CV in parentheses)

CA/OR thresher

shark/swordfish drift

gillnet fishery

1998-

2003

observer

data

20-23% 0 0,0,0,0,0 01

CA angel shark/halibut

and other species large 

mesh (>3.5") set gillnet 

fishery

1999 

2000 

2001 

2002 

2003

observer

data 

extrapolated 

estimate

4.0% 3

1.7%3

0.0%3 

0.0%3 

0.0%3

57 

24 

- 

- 

-

662 (0.10)1

415 (0.08)1

329 (0.09)1 

337 (0.11)1 

186 (0.09)1

386 (0.05)1

CA, OR, and WA salmon 

troll fishery

1990-92 logbook data - Avg. Annual

take = 7.33 n/a

CA herring purse seine 

fishery

1990-92 logbook data - Avg. Annual 

take = 0 n/a

CA anchovy, mackerel,

and tuna purse seine 

fishery

1990-92 logbook data - Avg. Annual

take = 0.67 n/a

WA, OR, CA groundfish 

trawl

1999 

2000 

2001 

2002 

2003 

1999-

2003

observer data

unmonitored 

hauls

68.6% 

80.6% 

96.2% 

100% 

100% 

0 

2 

0 

0 

0 

1

0 

3 (0.21)

0 

0 

0 

1

0.6 (0.21)

0.2 (n/a)

CA squid purse seine 

fishery

1997-

2001 logbook data

Warden obs 

2-3 

trips/month

0 Avg. Annual 

take = 0 n/a

(unknown net and hook

fisheries)

1999-

2003 stranding data 6 1.5

Total annual takes 388 (0.05)

1

The CA set gillnets were not observed after 1994, except for Monterey Bay, where the fishery was observed in 1999 and 2000. 

Mortality in other regions was extrapolated from current (1999-2003) effort estimates and 1990-94 entanglement rates, thus the CV of

the mortality estimate for this fishery is likely to be underestimated by an unknown amount. There was no observer coverage in this 

fishery in 2001-2003.

STATUS OF STOCK

A review of harbor seal dynamics through 1991 concluded that their status relative to OSP could 

not be determined with certainty (Hanan 1996). They are not listed as "endangered" or "threatened" under 

the Endangered Species Act nor as "depleted" under the MMPA. Total fishing mortality cannot be

accurately estimated for recent years, but extrapolations from past years indicate that fishing mortality (388 

per year) is less than the calculated PBR for this stock (1,896), and thus they would not be considered a

"strategic" stock under the MMPA. The average rate of incidental fishery mortality for this stock is likely

to be greater than 10% of the calculated PBR; therefore, fishery mortality cannot be considered

insignificant and approaching zero mortality and serious injury rate. The population appears to be

12
stabilizing at what may be their carrying capacity and the fishery mortality is declining. There are no 

known habitat issues that are of particular concern for this stock. Two unexplained harbor seal mortality 

events occurred in Point Reyes National Park involving at least 90 seals in 1997 and 16 seals in 2000. 

Necropsy of three seals in 2000 showed severe pneumonia; tests for morbillivirus were negative, but 

attempts are being made to identify another virus isolated from one of the three (F. Gulland, pers. comm.). 

All west-coast harbor seals that have been tested for morbilliviruses were found to be seronegative, 

indicating that this disease is not endemic in the population and that this population is extremely 

susceptible to an epidemic of this disease (Ham-Lammé et al. 1999). 

REFERENCES

Barlow, J., R. W. Baird, J. E. Heyning, K. Wynne, A. M. Manville, II, L. F. Lowry, D. Hanan, J. Sease, and 

V. N. Burkanov. 1994. A review of cetacean and pinniped mortality in coastal fisheries along the 

west coast of the U.S. and Canada and the east coast of the Russian Federation. Rep. Int. Whal. 

Commn, Special Issue 15:405-425. 

Bartholomew, G. A., R. A. Boolootian. 1960. Numbers and population structure of the pinnipeds on the 

California Channel Islands. J. Mammal. 41:366-375. 

Bonnot, P. 1928. Report on the seals and sea lions of California. Fish Bulletin Number 14. California 

Division of Fish and Game. 

Bonnot, P. 1951. The sea lions, seals and sea otter of the California coast. California Fish and Game 

37(4):371-389. 

Boveng, P. 1988. Status of the Pacific harbor seal population on the U.S. west coast. Admin. Rep. LJ-88-

06. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 43 pp. 

Brown, R. F. 1988. Assessment of pinniped populations in Oregon. Processed Report 88-05, National 

Marine Fisheries Service, Northwest and Alaska Fisheries Center, Seattle, Washington. 

Burg, T. M. 1996. Genetic analysis of eastern Pacific harbor seals (Phoca vitulina richardsi) from British 

Columbia and parts of Alaska using mitochondrial DNA and microsatellites. Masters Thesis, 

Univ. of British Columbia, Vancouver, British Columbia. 77pp. 

Calambokidis, J., S. M. Speich, J. Peard, G. H. Steiger, and J. C. Cubbage. 1985. Biology of Puget Sound 

marine mammals and marine birds: population health and evidence of pollution effects. U.S. 

Dep. Commer., NOAA Tech. Memo. NOS-OMA-18. 159 pp. 

Cameron, G. A. and K. A. Forney. 1999. Preliminary estimates of cetacean mortality in the California 

gillnet fisheries for 1997 and 1998. Paper SC/51/O4 presented to the International Whaling 

Commission, May 1999 (unpublished). 14 pp. 

Cameron, G.A. and K.A. Forney. 2000. Preliminary Estimates of Cetacean Mortality in California/Oregon 

Gillnet Fisheries for 1999. Paper SC/52/O24 presented to the International Whaling Commission, 

2000 (unpublished). 12 pp. Available from NMFS, Southwest Fisheries Science Center, P.O. Box 

271, La Jolla, California, 92038, USA. 

Carretta, J.V. 2001. Preliminary estimates of cetacean mortality in California gillnet fisheries for 2000. 

Report SC/53/SM9 presented to the Scientific Committee of the International Whaling 

Commission, June 2001 (unpublished). 21p. [Available from Southwest Fisheries Science Center, 

National Marine Fisheries Service, 8604 La Jolla Shores Dr., La Jolla, CA 92037, USA.] 

Carretta, J.V. 2002. Preliminary estimates of cetacean mortality in California gillnet fisheries for 2001. 

Report SC/54/SM12 presented to the Scientific Committee of the International Whaling 

Commission, April 2002 (unpublished). 22p. [Available from Southwest Fisheries Science 

Center, National Marine Fisheries Service, 8604 La Jolla Shores Dr., La Jolla, CA 92037, USA.] 

Carretta, J. V. and S. J. Chivers. 2003. Preliminary estimates of marine mammal mortality and biological 

sampling of cetaceans in California gillnet fisheries for 2002. Paper SC/55/SM3 presented to the 

International Whaling Commission (unpublished). 21pp. 

Carretta, J. V. and S. J. Chivers. 2004. Preliminary estimates of marine mammal mortality and biological 

sampling of cetaceans in California gillnet fisheries for 2003. Paper SC/56/SM1 presented to the 

International Whaling Commission (unpublished). 20pp. 

Forney, K.A., J. Barlow, M.M. Muto, M. Lowry, J. Baker, G. Cameron, J. Mobley, C. Stinchcomb, and 

J.V. Carretta. 2000. U.S. Pacific Marine Mammal Stock Assessments: 2000. U.S. Department of 

Commerce, NOAA Technical Memorandum NMFS-SWFSC-300. 276p. 

13
Ham-Lammé, K. D., D. P. King, B. C. Taylor, C. House, D. A. Jessup, S. Jeffries, P. K Yochem, F. M. D. 

Gulland, D. A. Ferrick, and J. L. Stott. 1999. The application of immuno-assays for serological 

detection of morbillivirus exposure in free ranging harbor seals (Phoca vitulina) and sea otters 

(Enhydra lutris) from the western coast of the United States. Mar. Mamm. Sci. 15(2):601-608. 

Hanan, D. A. 1993. Status of the Pacific harbor seal population on the coast of California in 1992. Final 

Report to the National Marine Fisheries Service, Southwest Region. 27pp. 

Hanan, D. A. 1996. Dynamics of Abundance and Distribution for Pacific Harbor Seal, Phoca vitulina 

richardsi, on the Coast of California. Ph.D. Dissertation, University of California, Los Angeles. 

158pp. 

Hanan, D. A., and S. L. Diamond. 1989. Estimates of sea lion, harbor seal, and harbor porpoise mortalities 

in California set net fisheries for the 1986-87 fishing year. Final Report. Cooperative agreement 

No. NA-86-ABH-00018. NOAA/NMFS SWR, January 1989. 10 pages. 

Hanan, D. A., D. B. Holts, and A. L. Coan, Jr. 1993. The California drift gill net fishery for sharks and 

swordfish, 1981-82 through 1990-91. Calif. Dept. Fish and Game Fish. Bull. No. 175. 95pp. 

Hanan, D. A., J. P. Scholl, and S. L. Diamond. 1988. Estimates of sea lion and harbor seal mortalities in 

California set net fisheries for 1983, 1984, and 1985. Final Report. Cooperative agreement No. 

NA-86-ABH-00018. NOAA/NMFS SWR October 1988. 10 pages. 

Herder, M. J. 1986. Seasonal movements and hauling site fidelity of harbor seals, Phoca vitulina richardsi, 

tagged at the Russian River, California. MS Thesis. Humbolt State Univ. 52 pages. 

Huber, H. 1995. The abundance of harbor seals (Phoca vitulina richardsi) in Washington, 1991-1993. 

MS Thesis, Univ. of Washington, Seattle, Washington. 56 pp. 

Huber, H., S. Jeffries, R. Brown, and R. DeLong. 1994. Harbor seal stock assessment in Washington and 

Oregon 1993. Annual report to the MMPA Assessment Program, Office of Protected Resources, 

NMFS, NOAA, 1335 East-West Highway, Silver Spring, MD 20910. 

Jeffries, S. J. 1985. Occurrence and distribution patterns of marine mammals in the Columbia River and 

adjacent coastal waters of northern Oregon and Washington. In: Marine Mammals and Adjacent 

Waters, 1980-1982. Processed Report 85-04, National Marine Fisheries Service, Northwest and 

Alaska Fisheries Center, Seattle, Washington. 

Julian, F. And M. Beeson. 1998. Estimates for marine mammal, turtle, and seabird mortality for two 

California gillnet fisheries: 1990-1995. Fish. Bull. 96:271-284. 

Kelly, B. P. 1981. Pelage polymorphism in Pacific harbor seals. Can. J. Zool. 59:1212-1219. 

Lowry, M.S., J.V. Carretta, and K.A. Forney. 2005. Pacific harbor seal, Phoca vitulina richardsi, census in 

California during May - July 2004. Administrative Report LJ-05-06, available from Southwest 

Fisheries Science Center, 8604 La Jolla Shores Drive, La Jolla, CA 92037. 38 p. 

Lamont, M. M., J. T. Vida, J. T. Harvey, S. Jeffries, R. Brown, H. H. Huber, R. DeLong, and W. K. 

Thomas. 1996. Genetic substructure of the Pacific harbor seal (Phoca vitulina richardsi) off 

Washington, Oregon, and California. Mar. Mamm. Sci. 12(3):402-413. 

Miller, D. J., M. J. Herder, and J. P. Scholl. 1983. California marine mammal-fishery interaction study, 

1979-1981. Admin. Rep. LJ-83-13C. Southwest Fisheries Science Center, National Marine 

Fisheries Service, P.O. Box 271, La Jolla, CA 92038. 233 pp. 

NMFS. 1995. Environmental assessment of proposed regulations to govern interactions between marine 

mammals and commercial fishing operations, under Section 118 of the Marine Mammal 

Protection Act. Department of Commerce, National Oceanic and Atmospheric Administration, 

National Marine Fisheries Service, Office of Protected Resources, June 1995. 139 p. + 4 

Appendices. 

O’Corry-Crowe, G. M., K. K. Martien, and B. L. Taylor. 2003. The analysis of population genetic structure 

in Alaskan harbor seals, Phoca vitulina, as a framework for the identification of management 

stocks. Administrative Report LJ-03-08. Southwest Fisheries Sceeince Center, 8604 La Jolla 

Shores Drive, La Jolla, CA, 92037. 

Perkins, P., J. Barlow, and M. Beeson. 1994. Report on pinniped and cetacean mortality in California 

gillnet fisheries: 1988-90. Admin. Rep. LJ-94-11. Southwest Fisheries Science Center, National 

Marine Fisheries Service, P. O. Box 271, La Jolla, California, 92038. 16 pp. 

Temte, J. L. 1986. Photoperiod and the timing of pupping in the Pacific harbor seal (Phoca vitulina 

richardsi) with notes on reproduction in northern fur seals and Dall’s porpoises. Masters Thesis, 

Oregon State Univ., Corvallis, Oregon. 

14
Westlake, R. L. and G. M. O’Corry-Crowe. 2002. Macrogeographic structure and patterns of genetic 

diversity in harbor seals (Phoca vitulina) from Alaska to Japan. Journal of Mammalogy 83(4): 

1111-1126. 

15
Revised 10/30/2007

HARBOR SEAL (Phoca vitulina richardsi): 

Oregon/Washington Coast Stock

STOCK DEFINITION AND GEOGRAPHIC RANGE

 Harbor seals inhabit coastal and estuarine waters off 

Baja California, north along the western coasts of the 

continental U.S., British Columbia, and Southeast Alaska, west 

through the Gulf of Alaska and Aleutian Islands, and in the 

Bering Sea north to Cape Newenham and the Pribilof Islands. 

They haul out on rocks, reefs, beaches, and drifting glacial ice 

and feed in marine, estuarine, and occasionally fresh waters. 

Harbor seals generally are non-migratory, with local movements 

associated with such factors as tides, weather, season, food 

availability, and reproduction (Scheffer and Slipp 1944; Fisher 

1952; Bigg 1969, 1981). Harbor seals do not make extensive 

pelagic migrations, though some long distance movement of 

tagged animals in Alaska (174 km) and along the U.S. west 

coast (up to 550 km) have been recorded (Pitcher and 

McAllister 1981, Brown and Mate 1983, Herder 1986). Harbor 

seals have also displayed strong fidelity for haulout sites 

(Pitcher and Calkins 1979, Pitcher and McAllister 1981). 

port considers only the Oregon/Washington Coast 

 For management purposes, differences in mean 

pupping date (Temte 1986), movement patterns (Jeffries 1985, 

Brown 1988), pollutant loads (Calambokidis et al. 1985), and 

fishery interactions have led to the recognition of three separate 

harbor seal stocks along the west coast of the continental U.S. 

(Boveng 1988): 1) inland waters of Washington State (including 

Hood Canal, Puget Sound, and the Strait of Juan de Fuca out to 

Cape Flattery), 2) outer coast of Oregon and Washington, and 3) 

California (Fig. 1). Recent genetic analyses provide additional 

support for this stock structure (Huber et al. 1994, Burg 1996, 

Lamont et al. 1996). Samples from Washington, Oregon, and 

California demonstrate a high level of genetic diversity and 

indicate that the harbor seals of Washington inland waters 

possess unique haplotypes not found in seals from the coasts of 

Washington, Oregon, and California (Lamont et al. 1996). This re

stock. Stock assessment reports for Washington Inland Waters and California harbor seals also appear in this 

volume. Harbor seal stocks that occur in the inland and coastal waters of Alaska are discussed separately in the 

Alaska Stock Assessment Reports. Harbor seals occurring in British Columbia are not included in any of the U.S. 

Marine Mammal Protection Act (MMPA) stock assessment reports. 

WA Inland stock

OR/WA

Coastal

stock

CA stock

Figure 1. Approximate distribution of 

harbor seals in the U.S. Pacific Northwest 

(shaded area). Stock boundaries separating 

the three stocks are shown. 

POPULATION SIZE

 Aerial surveys of harbor seals in Oregon and Washington were conducted by personnel from the National 

Marine Mammal Laboratory (NMML) and the Oregon and Washington Departments of Fish and Wildlife (ODFW 

and WDFW) during the 1999 pupping season. Total numbers of hauled-out seals (including pups) were counted 

during these surveys. In 1999, the mean count of harbor seals occurring along the Washington coast was 10,430 

(CV=0.14) animals (Jeffries et al. 2003). In 1999, the mean count of harbor seals occurring along the Oregon coast 

and in the Columbia River was 5,735 (CV=0.14) animals (Brown 1997; ODFW, unpubl. data). Combining these 

counts results in 16,165 (CV=0.10) harbor seals in the Oregon/Washington Coast stock. 

 Radio-tagging studies conducted at six locations (three Washington inland waters sites and three Oregon 

and Washington coastal sites) collected information on haulout patterns from 63 harbor seals in 1991 and 61 harbor 

seals in 1992. Haulout data from coastal and inland sites were not significantly different and were thus pooled, 

resulting in a correction factor of 1.53 (CV=0.065) to account for animals in the water which are missed during the 

aerial surveys (Huber et al. 2001). Using this correction factor results in a population estimate of 24,732 (16,165 x 

16
1.53; CV=0.12) for the Oregon/Washington Coast stock of harbor seals in 1999 (Jeffries et al. 2003; ODFW, 

unpubl. data). 

Minimum Population Estimate

 The minimum population estimate (NMIN) for this stock is calculated as the lower 20th percentile of the lognormal distribution of the 1999 population estimate of 24,732, which is 22,380 harbor seals. 

Current Population Trend

 Historical levels of harbor seal abundance in Oregon and Washington are unknown. The population 

apparently decreased during the 1940s 

and 1950s due to state-financed bounty 

programs. Approximately 17,133 harbor 

seals were killed in Washington by 

bounty hunters between 1943 and 1960 

(Newby 1973). More than 3,800 harbor 

seals were killed in Oregon between 1925 

and 1972 by bounty hunters and a statehired seal hunter (Pearson 1968). The 

population remained relatively low during 

the 1960s but, since the termination of the 

harbor seal bounty program and with the 

protection provided by the passage of the 

MMPA in 1972, harbor seal counts for 

this stock have increased from 6,389 in 

1977 to 16,165 in 1999 (Jeffries et al. 

2003; ODFW, unpubl. data). Based on 

the analyses of Jeffries et al. (2003) and 

Brown et al. (2005), both the Washington 

and Oregon portions of this stock have 

reached carrying capacity and are no 

longer increasing (Fig. 2). 

Washington Coast Harbor Seals

0

2000

4000

6000

8000

10000

12000

14000

1970 1975 1980 1985 1990 1995 2000 2005

Year

Count

CURRENT AND MAXIMUM NET 

PRODUCTIVITY RATES

 The Oregon/Washington Coast 

harbor seal stock increased at an annual 

rate of 7% from 1983 to 1992 and at 4% 

from 1983 to 1996 (Jeffries et al. 1997). 

Because the population was not at a very 

low level by 1983, the observed rates of 

increase may underestimate the maximum 

net productivity rate (RMAX). When a 

logistic model was fit to the Washington 

portion of the 1975-1999 abundance data, 

the resulting estimate of RMAX was 18.5% (95% CI = 12.9-26.8%) (Jeffries et al. 2003). When a logistic model was 

fit to the Oregon portion of the 1977-2003 abundance data, estimates of RMAX ranged from 6.4% (95% CI = 4.6-

27%) for the south coast of Oregon to 10.1% (95% CI = 8.6-20%) for the north coast (Brown et al. 2005). Until a 

combined analysis for the entire stock is completed, the pinniped default maximum theoretical net productivity rate 

(RMAX) of 12% will be used for this harbor seal stock (Wade and Angliss 1997). 

Oregon Harbor Seals

0

1000

2000

3000

4000

5000

6000

1970 1975 1980 1985 1990 1995 2000 2005

Year

Count

Figure 2. Generalized logistic growth curves of Washington 

Coast (Jeffries et al. 2003) and Oregon (Brown et al. 2005) harbor 

seals. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population 

estimate (22,380) times one-half the default maximum net growth rate for pinnipeds (1⁄2 of 12%) times a recovery 

factor of 1.0 (for stocks within OSP, Wade and Angliss 1997), resulting in a PBR of 1,343 harbor seals per year. 

17
HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fisheries Information

 Fishing effort in the northern Washington marine set gillnet fishery (areas 4, 4A, 4B, and 5) is conducted 

within the range of both stocks of harbor seals (Oregon/Washington Coast and Washington Inland Waters) occurring 

in Washington State waters. Some movement of animals between Washington’s coastal and inland waters is likely, 

although data from tagging studies have not shown movement of harbor seals between the two locations (Huber et 

al. 2001). For the purposes of this stock assessment report, the animals taken in waters south and west of Cape 

Flattery, WA (areas 4 and 4A), are assumed to have belonged to the Oregon/Washington Coast stock, and Table 1 

includes data only from that portion of the fishery. NMFS observers monitored 100% of the 50 net days (1 net day 

equals a 100-fathom length net set for 24 hours) of fishing effort in coastal waters in 2000; no fishing effort occurred 

in the coastal portion of the fishery in 2001-2003; and complete records of observer coverage and fishing effort in 

2004 are not available, but one vessel fished at least 60 net days in areas 4 and 4A and the vessel operator reported 

six harbor seal mortalities (Gearin et al. 1994, 2000; P. Gearin, unpubl. data; N. Pamplin, unpubl. data). The mean 

estimated mortality for this fishery in 2000-2004 is 0.8 (CV=0) harbor seals per year from observer data plus 1.2 

seals per year from fisher self-reports. 

 The WA/OR/CA groundfish trawl fishery (Pacific hake at-sea processing component) was monitored for 

incidental take during 2000-2004 (Perez 2003; J. Cusick, unpubl. data), and harbor seal mortalities occurred in 2000 

and 2004. The mean estimated mortality for this fishery in 2000-2004 is 0.6 (CV=0.35) harbor seals per year. 

Table 1. Summary of available information on the incidental mortality and serious injury of harbor seals 

(Oregon/Washington Coast stock) in commercial and tribal fisheries that might take this species and calculation of 

the mean annual mortality rate; n/a indicates that data are not available. Mean annual takes are based on 2000-2004 

data unless otherwise noted. 

Fishery name Years Data type

Percent 

observer 

coverage

Observed

mortality

Estimated

mortality

Mean annual takes 

(CV in parentheses)

Northern WA marine set 

gillnet (tribal fishery in 

coastal waters: areas 4 and 

4A)

2000 

2001 

2002 

2003 

2004 

2004

observer data 

fisher selfreports

100% 

no fishery 

no fishery 

no fishery 

unknown2

3 

0 

0 

0 

n/a 

6

3 (0) 

0 (0) 

0 (0) 

0 (0) 

n/a 

0.8 (0)1

>1.2 (n/a) 

WA/OR/CA groundfish 

trawl 

(Pacific hake at-sea 

processing component) 

2000 

2001 

2002 

2003 

2004

observer data 

80.6%3

96.2%3

100%4

100%4

100%4

2 

0 

0 

0 

1

2 (0.21) 

0 (0) 

0 (0) 

0 (0) 

1 (0)

0.6 (0.35) 

WA Grays Harbor salmon 

drift gillnet 1991-1993 observer data 4-5% 0, 1, 1 0, 10, 10 6.7 (0.50)

WA Willapa Bay drift gillnet 1991-1993 observer data 1-3% 0, 0, 0 0, 0, 0 0

WA Willapa Bay drift gillnet 1990-1993 fisher selfreports n/a 0, 0, 6, 8 n/a

≥3.5 (n/a )

see text

Unknown west coast 

fisheries 2000-2004 stranding data n/a 0, 0, 0, 4, 0 n/a ≥0.8 (n/a)

Minimum total annual takes >13.6 (0.41)

1

2000-2003 mortality estimates are included in the average. 2

Complete records of observer coverage in 2004 are not available. 

3

Percent observer coverage equals percent of observed catch; observers were present on 100% of the vessels. 4

Percent observer coverage equals percent of vessels with observers. 

18
 The Washington and Oregon Lower Columbia River drift gillnet fishery was monitored during the entire 

year in 1991-1993 (Brown and Jeffries 1993, Matteson et al. 1993c, Matteson and Langton 1994a). Harbor seal 

mortalities, incidental to the fishery, were observed only in the winter season and were extrapolated to estimate total 

harbor seal mortality. However, the structure of the fishery has changed substantially since the 1991-1992 fishing 

seasons, and this level of take no longer applies to the current fishery (see Appendix 1). The Oregon Department of 

Fish and Wildlife (ODFW) conducted test fisheries in the lower Columbia River in 2000-2002 to evaluate the use of 

small-mesh (31⁄2"-6") tangle (tooth) nets in commercial, spring chinook fisheries to effectively harvest target stocks, 

while allowing the live release of non-target stocks and species (G. Whisler, pers. comm.). An experimental 

commercial permit fishery and a full-fleet commercial demonstration fishery were also conducted in 2001 and 2002, 

respectively, to test the small-mesh gear. Due to high steelhead bycatch in the 2002 fishery, harvest managers used 

in-season test fishing during the 2003 and 2004 fishing seasons to determine the optimum timing and gear 

requirements for each subsequent full-fleet commercial fishing period. Both large-mesh (8-9.75”) and small-mesh 

tangle net (<4.25”) fishing periods were adopted in each year, although the 2003 season was severely curtailed to 

limit the catch of spring chinook stocks listed under the Endangered Species Act (ESA). With the focus on greater 

selectivity in winter/spring commercial salmon fisheries, levels of observer coverage were much higher in 2002-

2004 than in previous years. To meet management needs, this increased level of observer coverage in test fisheries 

and full-fleet commercial fisheries is expected to continue into the foreseeable future (J. North and G. Whisler, pers. 

comm.). Data on marine mammal interactions (predation, entanglement) recorded by observers during the permit 

and demonstration commercial fisheries in 2001-2002 and the full-fleet commercial fisheries in 2003-2004 have not 

yet been summarized; however, no marine mammal mortalities or serious injuries were reported to NMFS by vessel 

operators. 

 The Washington Grays Harbor salmon drift gillnet fishery was also monitored in 1991-1993 (Herczeg et al. 

1992a; Matteson and Molinaar 1992; Matteson et al. 1993a; Matteson and Langton 1994b, 1994c). During the 3-

year period, 98, 307, and 241 sets were monitored, representing approximately 4-5% observer coverage in each year. 

No mortalities were recorded in 1991. In 1992, observers recorded one harbor seal mortality incidental to the 

fishery, resulting in an extrapolated estimated total kill of 10 seals (CV=1.0). In 1993, observers recorded one 

harbor seal mortality incidental to the fishery, though a total kill was not extrapolated. Similar observer coverage in 

1992 and 1993 (4.2% and 4.4%, respectively) suggests that 10 is also a reasonable estimate of the total kill in 1993. 

Thus, the mean estimated mortality for this fishery in 1991-1993 is 6.7 (CV=0.50) harbor seals per year (Table 1). 

No observer data are available for this fishery after 1993, however, harbor seal takes are unlikely to have increased 

since the fishery was last observed, due to reductions in the number of participating vessels and available fishing 

time (see details in Appendix 1). Fishing effort and catch have declined throughout all salmon fisheries in the 

region due to management efforts to recover ESA-listed salmonids. 

 The Washington Willapa Bay drift gillnet fishery was also monitored at low levels of observer coverage in 

1991-1993 (Herczeg et al. 1992a, 1992b; Matteson and Molinaar 1992; Matteson et al. 1993b; Matteson and 

Langton 1994c, 1994d). In those years, 752, 576, and 452 sets were observed, representing approximately 2.5%, 

1.4%, and 3.1% observer coverage, respectively. No harbor seal mortalities were reported by observers. However, 

because mortalities were self-reported by fishers in 1992 and 1993, the low level of observer coverage failed to 

document harbor seal mortalities that had apparently occurred. Due to the low level of observer coverage for this 

fishery, the self-reported fishery mortalities have been included in Table 1 and represent a minimum mortality 

estimate resulting from that fishery (3.5 harbor seals per year). Harbor seal takes are unlikely to have increased 

since the fishery was last observed in 1993, due to reductions in the number of participating vessels and available 

fishing time (see details in Appendix 1). 

 Combining the estimates from the northern Washington marine set gillnet (0.8 from observer data + 1.2 

from fisher self-reports), WA/OR/CA groundfish trawl (0.6), Washington Grays Harbor salmon drift gillnet (6.7), 

and Washington Willapa Bay drift gillnet (3.5 from fisher self-reports) fisheries results in an estimated mean 

mortality rate of 12.8 harbor seals per year from these fisheries. 

 The Marine Mammal Authorization Program (MMAP) fisher self-reports, required of commercial vessel 

operators by the MMPA, are an additional source of information on the number of harbor seals killed or seriously 

injured incidental to commercial fishery operations. Between 2000 and 2004, there were no fisher self-reports of 

harbor seal mortalities from any MMAP-listed fishery operating in waters off the coasts of Oregon or Washington. 

Although these reports are considered incomplete (see details in Appendix 1), they represent a minimum mortality. 

In 2002 one harbor seal from this stock was reported incidentally taken in an in-river gillnet test fishery in southern 

Oregon, and one harbor seal mortality was reported in a Washington coastal river gillnet fishery in 2003. 

 Strandings of harbor seals entangled in fishing gear or with serious injuries caused by interactions with gear 

are a final source of fishery-related mortality information. A fishery-related stranding, in which four harbor seals 

19
were entangled in derelict gillnet gear in the Columbia River, was reported in 2003 (B. Norberg, pers. comm.). 

Since the gear could not be attributed to a particular fishery, these mortalities are listed in Table 1 as occurring in an 

unknown west coast fishery. Fishery-related strandings during 2000-2004 resulted in an estimated annual mortality 

of 0.8 harbor seals from this stock. This estimate is considered a minimum because not all stranded animals are 

found, reported, or examined for cause of death (via necropsy by trained personnel). 

Other Mortality

 According to Northwest Marine Mammal Stranding Network records, maintained by the NMFS Northwest 

Region, a total of eight human-caused harbor seal mortalities or serious injuries were reported from non-fisheries 

sources in 2000-2004. Seven animals were shot (one each in 2000 and 2004, two in 2001, and three in 2002) and 

one animal was struck by a boat in 2004, resulting in an estimated mortality of 1.6 harbor seals per year from this 

stock. This estimate is considered a minimum because not all stranded animals are found, reported, or examined for 

cause of death (via necropsy by trained personnel).

Subsistence Harvests by Northwest Treaty Indian Tribes

 Pacific Northwest treaty Indian tribes may have tribal regulations allowing tribal members to exercise 

treaty rights for subsistence harvest of harbor seals. There have been only a few reported takes of harbor seals from 

directed tribal subsistence hunts. It is possible that very few seals have been taken in directed hunts because tribal 

fishers use seals caught incidentally to fishing operations for their subsistence needs before undertaking a 

ceremonial or subsistence hunt. 

STATUS OF STOCK

 Harbor seals are not considered to be “depleted” under the MMPA or listed as “threatened” or 

“endangered” under the ESA. Based on currently available data, the level of human-caused mortality and serious 

injury (13.6 + 1.6 = 15.2) is not known to exceed the PBR (1,343). Therefore, the Oregon/Washington Coast stock 

of harbor seals is not classified as a “strategic” stock. The minimum total fishery mortality and serious injury for 

this stock (13.6: based on observer data (8.1) and self-reported fisheries information (4.7) or stranding data (0.8) 

where observer data were not available or failed to detect harbor seal mortalities) is less than 10% of the calculated 

PBR and, therefore, appears to be insignificant and approaching zero mortality and serious injury rate. The stock is 

within its Optimum Sustainable Population (OSP) level (Jeffries et al. 2003, Brown et al. 2005). 

REFERENCES

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Ridgway, S. H., and R. J. Harrison (eds.), Handbook of Marine Mammals. Vol. 2: Seals. Academic Press, 

New York. 359 pp. 

Boveng, P. 1988. Status of the Pacific harbor seal population on the U.S. west coast. Admin. Report LJ-88-06. 

Southwest Fisheries Center, National Marine Fisheries Service, P.O. Box 271, La Jolla, CA. 43 pp. 

Brown, R. F. 1988. Assessment of pinniped populations in Oregon: April 1984 to April 1985. NWAFC Processed 

Report 88-05. 44 pp. Available at National Marine Mammal Laboratory, 7600 Sand Point Way NE, 

Seattle, WA 98115. 

Brown, R. F. 1997. Abundance of Pacific harbor seals (Phoca vitulina richardsi) in Oregon: 1977-1996. Oregon 

Dept. Fish and Wildlife, Wildlife Diversity Program, Tech. Report No. 97-6-04. 12 pp. 

Brown, R. F., and S. J. Jeffries. 1993. Preliminary report on estimated marine mammal mortality in Columbia 

River fall and winter salmon gillnet fisheries, 1991-1992. Unpubl. Report. Columbia River Area Gillnet 

Fishery Observer Program. 13 pp. Available at Oregon Dept. Fish and Wildlife, 2040 SE Marine Science 

Dr., Newport, OR 97365. 

Brown, R. F., and B. R. Mate. 1983. Abundance, movements, and feeding habits of the harbor seal, Phoca vitulina, 

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seals in Oregon: 1977-2003. Mar. Mammal Sci. 21(4):657-670. 

Burg, T. M. 1996. Genetic analysis of eastern Pacific harbour seals (Phoca vitulina richardsi) from British 

Columbia and parts of Alaska using mitochondrial DNA and microsatellites. MS Thesis, Univ. of British 

Columbia, Vancouver, BC. 77 pp. 

20
Calambokidis, J., S. Speich, J. Peard, G. Steiger, D. M. Fry, J. Lowenstine, and J. Cubbage. 1985. Biology of Puget 

Sound marine mammals and marine birds: Population health and evidence of pollution effects. U.S. Dep. 

Commer., NOAA Tech. Memo. NOS-OMA-18. 159 pp. 

Cusick, J. West Coast Groundfish Observer Program, Fishery Resource Analysis and Monitoring Division, 

NWFSC, NMFS, 2725 Montlake Blvd. E, Seattle, WA 98112. 

Fisher, H. D. 1952. The status of the harbour seal in British Columbia, with particular reference to the Skeena 

River. Fish. Res. Bd. Can. Bull. 93. 58 pp. 

Gearin, P. J. National Marine Mammal Laboratory, AFSC, NMFS, 7600 Sand Point Way NE, Seattle, WA 98115. 

Gearin, P. J., S. R. Melin, R. L. DeLong, H. Kajimura, and M. A. Johnson. 1994. Harbor porpoise interactions with 

a chinook salmon set-net fishery in Washington State. Rep. Int. Whal. Commn. Special Issue 15:427-438. 

Gearin, P. J., M. E. Gosho, J. L. Laake, L. Cooke, R. L. DeLong, and K. M. Hughes. 2000. Experimental testing of 

acoustic alarms (pingers) to reduce bycatch of harbour porpoise, Phocoena phocoena, in the state of 

Washington. J. Cetacean Res. Manage. 2(1):1-9. 

Herczeg, K. M., A. A. Abajian, and V. M. C. Molinaar. 1992a. Summary report on the 1991 summer dip-in salmon 

gillnet fisheries in Willapa Bay and Grays Harbor. Unpubl. Report. Pacific States Marine Fisheries 

Commission, Astoria, OR. 10 pp. Available at PSMFC, 205 SE Spokane Street, Suite 100, Portland, OR 

97202. 

Herczeg, K. M., V. M. C. Molinaar, and A. A. Abajian. 1992b. Summary report on the 1991 fall Willapa Bay 

salmon gillnet fishery. Unpubl. Report. Pacific States Marine Fisheries Commission, Astoria, OR. 10 pp. 

Available at PSMFC, 205 SE Spokane Street, Suite 100, Portland, OR 97202. 

Herder, M. J. 1986. Seasonal movements and hauling site fidelity of harbor seals, Phoca vitulina richardsi, tagged 

at the Klamath River, California. MA Thesis, Humboldt State Univ., Arcata, CA. 52 pp. 

Huber, H., S. Jeffries, R. Brown, and R. DeLong. 1994. Harbor seal, Phoca vitulina richardsi, stock assessment in 

Washington and Oregon, 1993. 1993 Annual Report to the MMPA Assessment Program, Office of 

Protected Resources, NMFS, NOAA, 1335 East-West Highway, Silver Spring, MD 20910. Available at 

National Marine Mammal Laboratory, 7600 Sand Point Way NE, Seattle, WA 98115. 

Huber, H. R., S. J. Jeffries, R. F. Brown, R. L. DeLong, and G. VanBlaricom. 2001. Correcting aerial survey 

counts of harbor seals (Phoca vitulina richardsi) in Washington and Oregon. Mar. Mammal Sci. 

17(2):276-293. 

Jeffries, S. J. 1985. Occurrence and distribution patterns of marine mammals in the Columbia River and adjacent 

coastal waters of northern Oregon and Washington. Pp. 15-50, In: Beach, R. J., A. C. Geiger, S. J. Jeffries, 

S. D. Treacy, and B. L. Troutman, Marine mammals and their interactions with fisheries of the Columbia 

River and adjacent waters, 1980-1982. NWAFC Processed Report 85-04. 316 pp. Available at National 

Marine Mammal Laboratory, 7600 Sand Point Way NE, Seattle, WA 98115. 

Jeffries, S. J., R. F. Brown, H. R. Huber, and R. L. DeLong. 1997. Assessment of harbor seals in Washington and 

Oregon, 1996. Pp. 83-94, In: Hill, P. S., and D. P. DeMaster (eds.), MMPA and ESA Implementation 

Program, 1996. AFSC Processed Report 97-10. 255 pp. Available at National Marine Mammal 

Laboratory, 7600 Sand Point Way NE, Seattle, WA 98115. 

Jeffries, S., H. Huber, J. Calambokidis, and J. Laake. 2003. Trends and status of harbor seals in Washington State: 

1978-1999. J. Wildl. Manage. 67(1):208-219. 

Lamont, M. M., J. T. Vida, J. T. Harvey, S. Jeffries, R. Brown, H. H. Huber, R. DeLong, and W. K. Thomas. 1996. 

Genetic substructure of the Pacific harbor seal (Phoca vitulina richardsi) off Washington, Oregon, and 

California. Mar. Mammal Sci. 12(3):402-413. 

Matteson, K. M., and J. A. Langton. 1994a. Summary report on the 1993 fall Columbia River salmon gillnet 

fishery. Unpubl. Report. Pacific States Marine Fisheries Commission, Astoria, OR. 19 pp. Available at 

PSMFC, 205 SE Spokane Street, Suite 100, Portland, OR 97202. 

Matteson, K. M., and J. A. Langton. 1994b. Summary report on the 1993 fall Grays Harbor salmon gillnet fishery. 

Unpubl. Report. Pacific States Marine Fisheries Commission, Astoria, OR. 18 pp. Available at PSMFC, 

205 SE Spokane Street, Suite 100, Portland, OR 97202. 

Matteson, K. M., and J. A. Langton. 1994c. Summary report on the 1993 summer dip-in salmon gillnet fisheries in 

Willapa Bay and Grays Harbor. Unpubl. Report. Pacific States Marine Fisheries Commission, Astoria, 

OR. 22 pp. Available at PSMFC, 205 SE Spokane Street, Suite 100, Portland, OR 97202. 

Matteson, K. M., and J. A. Langton. 1994d. Summary report on the 1993 fall Willapa Bay salmon gillnet fishery. 

Unpubl. Report. Pacific States Marine Fisheries Commission, Astoria, OR. 18 pp. Available at PSMFC, 

205 SE Spokane Street, Suite 100, Portland, OR 97202. 

21
Matteson, K. M., and V. M. C. Molinaar. 1992. Summary report on the 1992 summer dip-in salmon gillnet 

fisheries in Willapa Bay and Grays Harbor. Unpubl. Report. Pacific States Marine Fisheries Commission, 

Astoria, OR. 13 pp. Available at PSMFC, 205 SE Spokane Street, Suite 100, Portland, OR 97202. 

Matteson, K. M., W. B. Barnett, and J. A. Langton. 1993a. Summary report on the 1992 fall Grays Harbor salmon 

gillnet fishery. Unpubl. Report. Pacific States Marine Fisheries Commission, Astoria, OR. 17 pp. 

Available at PSMFC, 205 SE Spokane Street, Suite 100, Portland, OR 97202. 

Matteson, K. M., W. B. Barnett, and J. A. Langton. 1993b. Summary report on the 1992 fall Willapa Bay salmon 

gillnet fishery. Unpubl. Report. Pacific States Marine Fisheries Commission, Astoria, OR. 17 pp. 

Available at PSMFC, 205 SE Spokane Street, Suite 100, Portland, OR 97202. 

Matteson, K. M., J. A. Langton, and R. L. Hadley. 1993c. Summary report on the 1993 winter Columbia River 

salmon gillnet fishery. Unpubl. Report. Pacific States Marine Fisheries Commission, Astoria, OR. 29 pp. 

Available at PSMFC, 205 SE Spokane Street, Suite 100, Portland, OR 97202. 

Newby, T. C. 1973. Changes in Washington State harbor seal population, 1942-1972. Murrelet 54:5-6. 

Norberg, B. National Marine Fisheries Service, Northwest Region, 7600 Sand Point Way NE, Seattle, WA 98115. 

North, J. Ocean Salmon and Columbia River Program, Oregon Department of Fish and Wildlife, 17330 SE Evelyn 

Street, Clackamas, OR 97015. 

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Pamplin, N. Makah Fisheries Management, P.O. Box 115, Neah Bay, WA 98357. 

Pearson, J. P. 1968. The abundance and distribution of harbor seals and Steller sea lions in Oregon. MS Thesis, 

Oregon State Univ., Corvallis, OR. 23 pp. 

Perez, M. 2003. Compilation of marine mammal incidental take data from the domestic and joint venture 

groundfish fisheries in the U.S. EEZ of the North Pacific, 1989-2001. U.S. Dep. Commer., NOAA Tech. 

Memo. NMFS-AFSC-138. 145 pp. 

Pitcher, K. W., and D. G. Calkins. 1979. Biology of the harbor seal (Phoca vitulina richardsi) in the Gulf of 

Alaska. U.S. Dep. Commer., NOAA, OCSEAP Final Report 19(1983):231-310. 

Pitcher, K. W., and D. C. McAllister. 1981. Movements and haul out behavior of radio-tagged harbor seals, Phoca 

vitulina. Can. Field Nat. 95:292-297. 

Scheffer, V. B., and J. W. Slipp. 1944. The harbor seal in Washington State. Amer. Midl. Nat. 32:373-416. 

Temte, J. L. 1986. Photoperiod and the timing of pupping in the Pacific harbor seal (Phoca vitulina richardsi) with 

notes on reproduction in northern fur seals and Dall porpoises. MS Thesis, Oregon State Univ., Corvallis, 

OR. 147 pp. 

Wade, P. R., and R. P. Angliss. 1997. Guidelines for assessing marine mammal stocks: Report of the GAMMS 

workshop April 3-5, 1996, Seattle, Washington. U.S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

Whisler, G. Ocean Salmon and Columbia River Program, Oregon Department of Fish and Wildlife, 17330 SE 

Evelyn Street, Clackamas, OR 97015. 

22
Revised 12/15/2003

HARBOR SEAL (Phoca vitulina richardsi): 

Washington Inland Waters Stock

STOCK DEFINITION AND GEOGRAPHIC RANGE

Harbor seals inhabit coastal and estuarine waters off 

Baja California, north along the western coasts of the 

continental U.S., British Columbia, and Southeast Alaska, west 

through the Gulf of Alaska and Aleutian Islands, and in the 

Bering Sea north to Cape Newenham and the Pribilof Islands. 

They haul out on rocks, reefs, beaches, and drifting glacial ice

and feed in marine, estuarine, and occasionally fresh waters. 

Harbor seals generally are non-migratory, with local

movements associated with such factors as tides, weather, 

season, food availability, and reproduction (Scheffer and Slipp

1944; Fisher 1952; Bigg 1969, 1981). Harbor seals do not 

make extensive pelagic migrations though some long distance

movement of tagged animals in Alaska (174 km) and along the 

U.S. west coast (up to 550 km) have been recorded (Pitcher and 

McAllister 1981, Brown and Mate 1983, Herder 1986). Harbor

seals have also displayed strong fidelity for haulout sites

(Pitcher and Calkins 1979, Pitcher and McAllister 1981). 

For management purposes, differences in mean 

pupping date (Temte 1986), movement patterns (Jeffries 1985,

Brown 1988), pollutant loads (Calambokidis et al. 1985) and 

fishery interactions have led to the recognition of three separate 

harbor seal stocks along the west coast of the continental U.S. 

(Boveng 1988): 1) inland waters of Washington State

(including Hood Canal, Puget Sound, and the Strait of Juan de 

Fuca out to Cape Flattery), 2) outer coast of Oregon and 

Washington, and 3) California (see Fig. 1). Recent genetic 

analyses provide additional support for this stock structure 

(Huber et al. 1994, Burg 1996, Lamont et al. 1996). Samples 

from Washington, Oregon, and California demonstrate a high

level of genetic diversity and indicate that the harbor seals of 

inland Washington waters possess unique haplotypes not found

in seals from the coasts of Washington, Oregon, and California 

(Lamont et al. 1996). In this report only the Washington Inland 

Waters stock is addressed. Harbor seal stocks that occur in the inland and coastal waters of Alaska are reported 

separately in the Stock Assessment Reports for the

WA Inland stock

OR/WA

Coastal

stock

CA stock

Figure 1. Approximate distribution of

harbor seals in the U.S. Pacific Northwest 

(shaded area). Stock boundaries separating 

the three stocks are shown. 

Alaska Region. 

POPULATION SIZE

Aerial surveys of harbor seals in Washington were conducted during the pupping season in 1999, during

which time the total number of hauled-out seals (including pups) were counted. In 1999, the mean count of harbor

seals occurring in Washington’s inland waters was 9,550 (CV=0.14) animals (Jeffries et al. 2003). 

Radio-tagging studies conducted at six locations (three Washington inland waters sites and three Oregon

and Washington coastal sites) collected information on haulout patterns from 63 harbor seals in 1991 and 61 harbor

seals in 1992. Data from coastal and inland sites were not significantly different and were thus pooled, resulting in a

correction factor of 1.53 (CV=0.065) to account for animals in the water which are missed during the aerial surveys

(Huber et al. 2001). Using this correction factor results in a population estimate of 14,612 (9,550 x 1.53; CV=0.15) 

for the Washington Inland Waters stock of harbor seals (Jeffries et al. 2003). 

Minimum Population Estimate

The log-normal 20th percentile of the 1999 population estimate for this stock is 12,844 harbor seals. 

23
Current Population Trend

Historical levels of harbor seal 

abundance in Washington are unknown.

The population apparently decreased

during the 1940s and 1950s due to a 

state-financed bounty program.

Approximately 17,133 harbor seals were

killed in Washington by bounty hunters 

between 1943 and 1960 (Newby 1973).

The population remained relatively low 

during the 1970s but, since the

termination of the harbor seal bounty

program in 1960 and with the protection

provided by the passage of the Marine

Mammal Protection Act (MMPA) in 

1972, harbor seal numbers in

Washington have increased (Jeffries

1985). 

0

2000

4000

6000

8000

10000

12000

14000

1975 1980 1985 1990 1995 2000

Year

Total count

Between 1983 and 1996, the 

annual rate of increase for this stock was 

6% (Jeffries et al. 1997). The peak count

occurred in 1996 and, based on a fitted 

generalized logistic model (Fig. 2), the

population is thought to be stable (Jeffries

et al. 2003). 

Figure 2. Generalized logistic population growth curve for the

Washington Inland Waters stock of harbor seals, 1978-1999 

(Jeffries et al. 2003).

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

From 1991 to 1996, counts of harbor seals in Washington State have increased at an annual rate of 10% 

(Jeffries et al. 1997). Because the population was not at a very low level by 1991, the observed rate of increase may 

underestimate the maximum net productivity rate (RMAX). When a logistic model was fit to the 1978-1999 

abundance data, the resulting estimate of RMAX was 12.6% (95% CI = 9.4-18.7%) (Jeffries et al. 2003). This value 

of RMAX is very close to the default pinniped maximum theoretical net productivity rate of 12% (RMAX), therefore, 

12% will be employed for this harbor seal stock (Wade and Angliss 1997). 

POTENTIAL BIOLOGICAL REMOVAL

The potential biological removal (PBR) level for this stock is calculated as the minimum population size 

(12,844) times one-half the default maximum net growth rate for pinnipeds (1⁄2 of 12%) times a recovery factor of 

1.0 (for stocks within OSP, Wade and Angliss 1997), resulting in a PBR of 771 harbor seals per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fisheries Information

NMFS observers monitored the northern Washington marine set gillnet fishery in 1997, 1998, and 2000;

there was no observer coverage in 1999 or 2001 (Gearin et al. 1994, 2000; P. Gearin, unpubl. data). For the entire 

fishery (coastal + inland waters), observer coverage ranged from approximately 40 to 98% during observed years.

Fishing effort is conducted within the range of both stocks of harbor seals (Oregon/Washington Coast and 

Washington Inland Waters stocks) occurring in Washington State waters. For the purposes of this stock assessment

report, the animals taken in the inland portion of the fishery are assumed to have belonged to the Washington Inland 

Waters stock and the animals taken in the coastal portion of the fishery are assumed to have belonged to the

Oregon/Washington Coast stock. Some movement of animals between Washington’s coastal and inland waters is

likely, although data from tagging studies have not shown movement of harbor seals between the two locations

(Huber et al. 2001). Accordingly, Table 1 includes data only from that portion of the northern Washington marine

set gillnet fishery occurring within the range of the Washington Inland Waters stock (those waters east of Cape

Flattery), where observer coverage ranged from 40 to 80% between 1997 and 2001 and fishing effort ranged from 4-

46 net days per year (1 net day equals a 100-fathom length net In 1993, as a pilot for future observer programs, 

NMFS, in conjunction with the Washington Department of Fish and Wildlife (WDFW) monitored all non-treaty 

components of the Washington Puget Sound Region salmon gillnet fishery (Pierce et al. 1994). Observer coverage

24
was 1.3% overall, ranging from 0.9% to 7.3% for the various components of the fishery. Two harbor seal 

mortalities were reported (Table 1). Pierce et al. (1994) cautioned against extrapolating these mortalities to the 

entire Puget Sound fishery due to the low observer coverage and potential biases inherent in the data. The area 7/7A 

sockeye landings represented the majority of the non-treaty salmon landings in 1993, approximately 67%. Results 

of this pilot study were used to design the 1994 observer programs discussed below. 

Table 1. Summary of available information on the incidental mortality and injury of harbor seals (Washington 

Inland Waters stock) in commercial and tribal fisheries that might take this species and calculation of the mean 

annual mortality rate; n/a indicates that data are not available. All entanglements resulted in the death of the animal. 

Mean annual takes are based on 1997-2001 data unless noted otherwise. 

Fishery name Years

Data 

type

Percent 

observer 

coverage

Observed

mortality

Estimated

mortality

Mean annual 

takes (CV in 

parentheses)

Northern WA marine set gillnet 

(tribal fishery in inland waters: 

areas 4B and 5)

97 

98 

99 

00 

01 

97-01

obs data 

selfreports

80% 

40% 

0% 

58% 

0% 

0 

0 

n/a 

0 

n/a 

0, 0, 0, 0, 2

0 

0 

n/a 

0 

n/a 

01

≥0.4 (n/a)

WA Puget Sound Region salmon 

set/drift gillnet (observer programs 

listed below covered segments of 

this fishery):

- - - - - -

Puget Sound non-treaty salmon 

gillnet (all areas and species) 93 obs data 1.3% 2 n/a see text

Puget Sound non-treaty chum 

salmon gillnet (areas 10/11 and 

12/12B)

94 obs data 11% 1 10 10 (n/a)

Puget Sound treaty chum 

salmon gillnet (areas 12, 12B, 

and 12C)

94 obs data 2.2% 0 0 0

Puget Sound treaty chum and 

sockeye salmon gillnet (areas 

4B, 5, and 6C)

94 obs data 7.5% 0 0 0

Puget Sound treaty and nontreaty sockeye salmon gillnet 

(areas 7 and 7A)

94 obs data 7% 1 15 15 (1.0)

WA salmon net pens 97-01 self 

reports n/a 10, 5, 0, 0, 0 n/a ≥3 (n/a)

Unknown Puget Sound fishery 97-01 stran d

data n/a 1, 1, 0, 2, 2 n/a ≥1.2 (n/a)

Minimum total annual takes ≥29.6 (1.0)

1

1997-98 and 2000 mortality estimates are included in the average.

 

 In 1994, NMFS, in conjunction with WDFW conducted an observer program during the Puget Sound nontreaty chum salmon gillnet fishery (areas 10/11 and 12/12B). A total of 230 sets were observed during 54 boat trips, 

representing approximately 11% observer coverage of the 500 fishing boat trips comprising the total effort in this 

fishery, as estimated from fish ticket landings (Erstad et al. 1996). One harbor seal was taken in the fishery, 

resulting in an entanglement rate of 0.02 harbor seals per trip (0.004 harbor seals per set), which extrapolated to 

approximately 10 mortalities for the entire fishery. The Puget Sound treaty chum salmon gillnet fishery in Hood 

Canal (areas 12, 12B, and 12C) and the Puget Sound treaty sockeye/chum gillnet fishery in the Strait of Juan de 

25
Fuca (areas 4B, 5, and 6C) were also monitored in 1994 (NWIFC 1995). No harbor seal mortalities were reported in 

the observer programs covering these treaty salmon gillnet fisheries, where observer coverage was estimated at 2.2% 

(based on % of total catch observed) and approximately 7.5% (based on % of observed trips to total landings), 

respectively. 

 Also in 1994, NMFS, in conjunction with WDFW and the Tribes, monitored the Puget Sound treaty and 

non-treaty sockeye salmon gillnet fishery (areas 7 and 7A). During this fishery, observers monitored 2,205 sets, 

representing approximately 7% of the estimated number of sets in the fishery (Pierce et al. 1996). There was one 

observed harbor seal mortality (two others were entangled and released unharmed), resulting in a mortality rate of 

0.00045 harbor seals per set, which was extrapolated to 15 mortalities (CV=1.0) for the entire fishery. 

 In 1996, Washington Sea Grant Program conducted a test fishery in the non-treaty sockeye salmon gillnet 

fishery (area 7) to compare entanglement rates of seabirds and marine mammals and catch rates of salmon using 

three experimental gears and a control (monofilament mesh net). The experimental nets incorporated highly visible 

mesh in the upper quarter (50 mesh gear) or upper eighth (20 mesh gear) of the net or had low-frequency sound 

emitters attached to the corkline (Melvin et al. 1997). In 642 sets during 17 vessel trips, there were two harbor seal 

mortalities (one other was released alive with no apparent injuries). 

 Combining the estimates from the northern Washington marine set gillnet fishery (0.4), the Puget Sound 

non-treaty chum salmon gillnet fishery in areas 10/11 and 12/12B (10), and the Puget Sound treaty and non-treaty 

sockeye salmon gillnet fishery in areas 7 and 7A (15) results in an estimated minimum annual mortality rate in 

observed fisheries of 25.4 harbor seals from this stock. It should be noted that the 1994 observer programs did not 

sample all segments of the Washington Puget Sound Region salmon set/drift gillnet fishery and, further, the 

extrapolations of total kill did not include effort for the unobserved segments of this fishery. Therefore, 25.4 is an 

underestimate of the harbor seal mortality due to the entire fishery. The percentage of the overall Washington Puget 

Sound Region salmon set/drift gillnet fishery effort that was observed in 1994 was not quantified. However, the 

areas having the highest salmon catches and in which a majority of the vessels operated in 1994 were covered by the 

1994 observer programs (J. Scordino, pers. comm.). Harbor seal takes in the Washington Puget Sound Region 

salmon drift gillnet fishery are unlikely to have increased since the fishery was last observed in 1994, due to 

reductions in the number of participating vessels and available fishing time (see details in Appendix 1). Fishing 

effort and catch have declined throughout all salmon fisheries in the region due to management efforts to recover 

ESA-listed salmonids. 

 An additional source of information on the number of harbor seals killed or injured incidental to 

commercial fishery operations is the self-reported fisheries information required of vessel operators by the MMPA. 

During the period between 1994 and 2001, there were no fisher self-reports of harbor seal mortalities from the 

Washington Puget Sound Region salmon set/drift gillnet fishery. Unlike the 1994 observer program data, the selfreported fishery data cover the entire fishery (including treaty and non-treaty components). There were fisher selfreports of 15 harbor seal mortalities due to entanglement in Washington salmon net pens in 1997-2001, 10 in 1997 

and five in 1998 (Table 1), resulting in an estimated annual mortality of three harbor seals from this stock. 

However, because logbook records (fisher self-reports required during 1990-94) are most likely negatively biased 

(Credle et al. 1994), these are considered to be minimum estimates. Logbook data are available for part of 1989-

1994, after which incidental mortality reporting requirements were modified. Under the new system, logbooks are 

no longer required; instead, fishers provide self-reports. Data for the 1994-1995 phase-in period is fragmentary. 

After 1995, the level of reporting dropped dramatically, such that the records are considered incomplete and 

estimates of mortality based on them represent minimums (see Appendix 7 in Angliss et al. 2001 for details). 

 Strandings of harbor seals entangled in fishing gear or with injuries caused by interactions with gear are a 

final source of fishery-related mortality information. During the period from 1997 to 2001, small numbers of 

fishery-related strandings of harbor seals have occurred in most years (B. Norberg, pers. comm.). As the strandings 

could not be attributed to a particular fishery, they have been included in Table 1 as occurring in an unknown Puget 

Sound fishery. Fishery-related strandings during 1997-2001 resulted in an estimated annual mortality of 1.2 harbor 

seals from this stock. This estimate is considered a minimum because not all stranded animals are found, reported, 

or examined for cause of death (via necropsy by trained personnel). 

 The minimum estimated fishery mortality and serious injury for this stock is 29.6 harbor seals per year, 

based on observer program data (25.4), fisher self-reports (3), and stranding data (1.2). 

Other Mortality

 According to Northwest Marine Mammal Stranding Network records, maintained by the NMFS Northwest 

Region, a total of 18 human-caused harbor seal mortalities or serious injuries were reported from non-fisheries 

sources in 1997-2001. Fifteen animals were shot (seven, two, one, three and two each year, respectively), two were 

26
struck by ships (one each in 1999 and 2001), and one was found with neck injuries in 1999, resulting in an estimated 

mortality of 3.6 harbor seals per year from this stock. This estimate is considered a minimum because not all 

stranded animals are found, reported, or cause of death determined (via necropsy by trained personnel). 

Subsistence Harvests by Northwest Treaty Indian Tribes

 Several Pacific Northwest treaty Indian tribes have promulgated tribal regulations allowing tribal members 

to exercise treaty rights for subsistence harvest of harbor seals. There have been only a few reported takes of harbor 

seals from directed tribal subsistence hunts. It is possible that very few seals have been taken in directed hunts 

because tribal fishers use seals caught incidentally to fishing operations, in the northern Washington marine set 

gillnet and Washington Puget Sound Region treaty salmon gillnet fisheries, for their subsistence needs before 

undertaking a ceremonial or subsistence hunt. From communications with the tribes, the NMFS Northwest Regional 

Office (J. Scordino, pers. comm.) believes that 0-5 harbor seals from this stock may be taken annually in directed 

subsistence harvests. 

STATUS OF STOCK

 Harbor seals are not considered to be “depleted” under the MMPA or listed as “threatened” or 

“endangered” under the Endangered Species Act. Based on currently available data, the level of human-caused 

mortality and serious injury (29.6 + 3.6 + 0-5 = 33.2-38.2) is not known to exceed the PBR (771). Therefore, the 

Washington Inland Waters stock of harbor seals is not classified as a “strategic” stock. At present, the minimum 

estimated fishery mortality and serious injury for this stock (29.6) appears to be less than 10% of the calculated PBR 

(77) and, therefore, appears to be insignificant and approaching zero mortality and serious injury rate. The stock is 

within its Optimum Sustainable Population (OSP) level (Jeffries et al. 2003). 

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Bigg, M. A. 1981. Harbour seal, Phoca vitulina, Linnaeus, 1758 and Phoca largha, Pallas, 1811. Pp. 1-27, In:

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and Alaska Fisheries Science Center, Seattle, WA. 

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at Netarts and Tillamook Bays, Oregon. Fish. Bull. 81:291-301. 

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Columbia and parts of Alaska using mitochondrial DNA and microsatellites. MS Thesis, Univ. of British 

Columbia, Vancouver, BC. 77 pp. 

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November 10-11, 1993. U.S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR-94-1. 96 pp. 

Erstad, P., S. J. Jeffries, and D. J. Pierce. 1996. 1994 Report for the Puget Sound fishery observer program in 

management areas 10/11 & 12/12B: nontreaty chum gill net fishery. Final Report, Washington Dept. Fish 

and Wildlife, Olympia, WA. 14 pp. 

Fisher, H. D. 1952. The status of the harbour seal in British Columbia, with particular reference to the Skeena 

River. Fish. Res. Bd. Can. Bull. 93. 58 pp. 

Gearin, P. J. National Marine Mammal Laboratory, AFSC, NMFS, 7600 Sand Point Way NE, Seattle, WA 98115. 

Gearin, P. J., S. R. Melin, R. L. DeLong, H. Kajimura, and M. A. Johnson. 1994. Harbor porpoise interactions with 

a chinook salmon set-net fishery in Washington State. Rep. Int. Whal. Commn. Special Issue 15:427-438. 

Gearin, P. J., M. E. Gosho, J. L. Laake, L. Cooke, R. L. DeLong, and K. M. Hughes. 2000. Experimental testing of 

acoustic alarms (pingers) to reduce bycatch of harbour porpoise, Phocoena phocoena, in the state of 

Washington. J. Cetacean Res. Manage. 2(1):1-9. 

27
Herder, M. J. 1986. Seasonal movements and hauling site fidelity of harbor seals, Phoca vitulina richardsi, tagged 

at the Russian River, California. MS Thesis, Humbolt State Univ., Humbolt, CA. 52 pp. 

Huber, H., S. Jeffries, R. Brown, and R. DeLong. 1994. Harbor seal, Phoca vitulina richardsi, stock assessment in 

Washington and Oregon, 1993. 1993 Annual Report to the MMPA Assessment Program, Office of 

Protected Resources, NMFS, NOAA, 1335 East-West Highway, Silver Spring, MD 20910. Available at 

National Marine Mammal Laboratory, 7600 Sand Point Way NE, Seattle, WA 98115. 

Huber, H. R., S. J. Jeffries, R. F. Brown, R. L. DeLong, and G. VanBlaricom. 2001. Correcting aerial survey 

counts of harbor seals (Phoca vitulina richardsi) in Washington and Oregon. Mar. Mammal. Sci. 

17(2):276-293. 

Jeffries, S. J. 1985. Occurrence and distribution patterns of marine mammals in the Columbia River and adjacent 

coastal waters of northern Oregon and Washington. In: Marine mammals and their interactions with 

fisheries of the Columbia River and adjacent waters, 1980-1982. Processed Report 85-04, NMFS, 

Northwest and Alaska Fisheries Center, Seattle, WA. 

Jeffries, S. J., R. F. Brown, H. R. Huber, and R. L. DeLong. 1997. Assessment of harbor seals in Washington and 

Oregon, 1996. Pp. 83-94, In: Hill, P. S., and D. P. DeMaster (eds.), MMPA and ESA Implementation 

Program, 1996. AFSC Processed Report 97-10. 255 pp. Available at National Marine Mammal 

Laboratory, 7600 Sand Point Way NE, Seattle, WA 98115. 

Jeffries, S., H. Huber, J. Calambokidis, and J. Laake. 2003. Trends and status of harbor seals in Washington State: 

1978-1999. J. Wildl. Manage. 67(1):208-219. 

Lamont, M. M., J. T. Vida, J. T. Harvey, S. Jeffries, R. Brown, H. H. Huber, R. DeLong, and W. K. Thomas. 1996. 

Genetic substructure of the Pacific harbor seal (Phoca vitulina richardsi) off Washington, Oregon, and 

California. Mar. Mammal Sci. 12(3):402-413. 

Melvin, E. F., L. L. Conquest, and J. K. Parrish. 1997. Seabird bycatch reduction: new tools for Puget Sound drift 

gillnet salmon fisheries. 1996 Sockeye and 1995 Chum Salmon Test Fisheries Final Report. Washington 

Sea Grant Program, Seattle, WA. 48 pp. 

Newby, T. C. 1973. Changes in Washington State harbor seal population, 1942-1972. Murrelet 54:5-6. 

Norberg, B. National Marine Fisheries Service, Northwest Region, 7600 Sand Point Way NE, Seattle, WA 98115. 

Northwest Indian Fisheries Commission (NWIFC). 1995. Monitoring of marbled murrelet and marine mammal 

interactions with 1994 tribal gillnet fisheries in northern Puget Sound, Hood Canal, and the Strait of Juan 

de Fuca. Final Report to NMFS (Contract No. 52ABNF400087) and U.S. Fish and Wildlife Service. 

Unpubl. report. 41 pp. Available at NWIFC, 6730 Martin Way E, Olympia, WA 98516. 

Pierce, D. J., W. P. Ritchie, and R. Kreuziger. 1994. Preliminary findings of seabird interactions with the nontreaty salmon gill net fishery: Puget Sound and Hood Canal Washington. Unpubl. report. Washington 

Dept. Fish and Wildlife, Olympia, WA. 39 pp. Available at WDFW, 600 Capitol Way N, Olympia, WA 

98501. 

Pierce, D. J., M. Alexandersdottir, S. J. Jeffries, P. Erstad, W. Beattie, and A. Chapman. 1996. Interactions of 

marbled murrelets and marine mammals with the 1994 Puget Sound sockeye gill net fishery. Final Report, 

Washington Dept. Fish and Wildlife, Olympia, WA. 21 pp. 

Pitcher, K. W., and D. G. Calkins. 1979. Biology of the harbor seal (Phoca vitulina richardsi) in the Gulf of 

Alaska. U.S. Dep. Commer., NOAA, OCSEAP Final Rep. 19(1983):231-310. 

Pitcher, K. W., and D. C. McAllister. 1981. Movements and haul out behavior of radio-tagged harbor seals, Phoca 

vitulina. Can. Field Nat. 95:292-297. 

Scheffer, V. B., and J. W. Slipp. 1944. The harbor seal in Washington State. Amer. Midl. Nat. 32:373-416. 

Scordino, J. National Marine Fisheries Service, Northwest Region, 7600 Sand Point Way NE, Seattle, WA 98115. 

Temte, J. L. 1986. Photoperiod and the timing of pupping in the Pacific harbor seal (Phoca vitulina richardsi) with 

notes on reproduction in northern fur seals and Dall's porpoises. MS Thesis, Oregon State Univ., Corvallis, 

OR. 

Wade, P. R., and R. Angliss. 1997. Guidelines for assessing marine mammal stocks: report of the GAMMS 

workshop April 3-5, 1996, Seattle, Washington. U.S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

28
Revised 10/30/2007

NORTHERN ELEPHANT SEAL (Mirounga angustirostris): 

California Breeding Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

Northern elephant seals breed and give 

birth in California (U.S.) and Baja California 

(Mexico), primarily on offshore islands (Stewart et 

al. 1994), from December to March (Stewart and 

Huber 1993). Males feed near the eastern Aleutian 

Islands and in the Gulf of Alaska, and females 

feed further south, south of 45o

N (Stewart and 

Huber 1993; Le Boeuf et al. 1993). Adults return 

to land between March and August to molt, with 

males returning later than females. Adults return 

to their feeding areas again between their 

spring/summer molting and their winter breeding 

asons.

tion is considered here to be a separate stock.

se 

 Populations of northern elephant seals in 

the U.S. and Mexico were all originally derived 

from a few tens or a few hundreds of individuals 

surviving in Mexico after being nearly hunted to 

extinction (Stewart et al. 1994). Given the very 

recent derivation of most rookeries, no genetic 

differentiation would be expected. Although 

movement and genetic exchange continues 

between rookeries, most elephant seals return to 

their natal rookeries when they start breeding 

(Huber et al. 1991). The California breeding 

population is now demographically isolated from 

the Baja California population. No international 

agreements exist for the joint management of this 

species by the U.S. and Mexico. The California 

breeding popula

W130 W125 W120 W115 W110 W105 W100

Longitude

N15

N20

N25

N30

N35

N40

N45

Latitude

WASHINGTON

OREGON

CALIFORNIA

MEXICO

UNITED STATES

PACIFIC OCEAN

CALIFORNIA BREEDING

 STOCK

 Isla 

Cedros

Isla Guadalupe

Isla Benito

 Del Este

SE Farallon Is.

Ano Nuevo

Channel

 Islands

Figure 1. Stock boundary and major rookery 

areas for northern elephant seals in the U.S. and 

Mexico.

POPULATION SIZE

A complete population count of elephant seals is not possible because all age classes are not 

ashore at the same time. Elephant seal population size is typically estimated by counting the number of 

pups produced and multiplying by the inverse of the expected ratio of pups to total animals (McCann 

1985). Stewart et al. (1994) used McCann's multiplier of 4.5 to extrapolate from 28,164 pups to a 

population estimate of 127,000 elephant seals in the U.S. and Mexico in 1991. The multiplier of 4.5 was 

based on a non-growing population. Boveng (1988) and Barlow et al. (1993) suggest that a multiplier of 

3.5 is more appropriate for a rapidly growing population such as the California stock of elephant seals. 

Based on the estimated 35,549 pups born in California in 2005 (Fig. 2) and this 3.5 multiplier, the 

California stock was approximately 124,000 in 2005. 

Minimum Population Estimate

The minimum population size for northern elephant seals can be estimated very conservatively as 

74,913, which is equal to twice the observed pup count (to account for the pups and their mothers) plus 

3,815 males and juveniles counted at the Channel Islands and central California sites in 2005 (Mark 

Lowry, NMFS unpubl. data) . More sophisticated methods of estimating minimum population size could 

be applied if the variance of the multiplier used to estimate population size were known. 

29
Current Population Trend

 Based on trends 

in pup counts, northern 

elephant seal colonies 

were continuing to grow 

in California through 2005 

(Figure 2), but appear to 

be stable or slowly 

decreasing in Mexico 

(Stewart et al. 1994). 

 

CURRENT AND 

Although growth 

rates as 

stic growth model 

OTENTIAL BIOLOGICAL REMOVAL

BR) level for this stock is calculated as the minimum 

latio

MAXIMUM NET 

PRODUCTIVITY 

RATE

high as 16% per 

year have been 

documented for elephant 

seal rookeries in the U.S. 

from 1959 to 1981 

(Cooper and Stewart 

1983), much of this 

growth was supported by 

immigration from Mexico. 

The highest growth rate 

measured for the whole 

U.S./Mexico population 

was 8.3% between 1965 and

indicates that the maximum population growth rate (R

Northern Elephant Seal Births in U.S.

0

5,000

10,000

15,000

20,000

25,000

30,000

35,000

40,000

1950 1960 1970 1980 1990 2000 2010

Year

# Births

Total (U.S.)

Channel Islands

Central California

Figure 2. Estimated number of northern elephant seal births in California 

1958-2005. Multiple independent estimates are presented for the Channel 

Islands 1988-91. Estimates are from Stewart et al. (1994), Lowry et al. 

(1996), Lowry (2002) and unpublished data from Sarah Allen, Dan 

Crocker, Brian Hatfield, Ron Jameson, Bernie Le Boeuf, Mark Lowry, Pat 

Morris, Guy Oliver, Derek Lee, and William Sydeman. 

 1977 (Cooper and Stewart 1983). A generalized logi

max) is 11.7 percent (SE = 2.7) (Figure 3). 

P

 The potential biological removal (P

popu n size (74,913) times one half the observed maximum net growth rate for this stock (1⁄2 of 11.7%) 

times a recovery factor of 1.0 (for a stock of unknown status that is increasing, Wade and Angliss 1997) 

resulting in a PBR of 4,382. 

HUMAN-CAUSED MORTALITY

own fishery mortality and injury for this stock of northern elephant seals is given 

 Table

Fisheries Information

 A summary of kn

in 1. More detailed information on these fisheries is provided in Appendix 1. Stranding data 

reported to the California, Oregon, and Washington Marine Mammal Stranding Networks in 2000-2004 

include elephant seal injuries caused by hook-and-line fisheries (two injuries) and gillnet fisheries (one 

injury). 

30
Table 1. Summary of available information on the mortality and serious injury of northern elephant seals 

(California breeding stock) in commercial fisheries that might take this species (Carretta and Chivers 2004, 

Carretta et al. 2005a, 2005b, Perez 2003 , Perez 2003; Perez, in prep.; NMFS unpubl. data). n/a indicates 

information is not available. Mean annual takes are based on 2000-2004 data unless noted otherwise. 

Fishery Name Year(s) Data Type

Percent 

Observer 

Coverage

Observed

Mortality

Estimated 

Mortality (CV in 

parentheses)

Mean 

Annual Takes 

(CV in 

parentheses)

CA/OR thresher 

shark/swordfish drift 

gillnet fishery 

2000 

2001 

2002 

2003 

2004 

observer 

data 

22.9% 

20.4% 

22.1% 

20.2% 

20.6%

6 

1 

1 

1 

0 

26 (0.39) 

5 (0.94) 

5 (0.92) 

5 (1.00) 

0 

8 (0.40) 

CA angel shark/halibut 

and other species large 

mesh (>3.5") set gillnet 

fishery1

20011

20021

20031

20041

20051

observer 

data 

0% 

0% 

0% 

0% 

0% 

n/a 

n/a 

n/a 

n/a 

n/a 

n/a 

n/a 

n/a 

n/a 

n/a 

n/a

WA, OR, CA domestic 

groundfish trawl (At-sea 

processing Pacific 

whiting fishery only) 

2000 

2001 

2002 

2003 

2004 

observer 

data 

80.6% 

96.2% 

100% 

100% 

100% 

1 

0 

0 

0 

3 

1 (n/a) 

0 (n/a) 

0 (n/a) 

0 (n/a) 

3 (n/a) 

0.8 (n/a) 

WA, OR, CA domestic 

groundfish trawl fishery 

(bottom trawl) 

2000-2004 observer n/a 0 0 0 (n/a) 

Total annual takes > 8.8 (0.40)

1

 The most recent observer data for the halibut set gillnet fishery is from 2000 in Monterey Bay only and there has not been a fisherywide observer program since 1990-94. There are no current estimates of mortality for this fishery, as this would require assuming that 

current kill rates are comparable to kill rates observed between 1990-94 and extrapolation of mortality estimates using current

estimates of fishing effort. 

 

Although all of the mortalities in Table 1 occurred in U.S. waters, some may be of seals from 

Mexico's breeding population that are migrating through U.S. waters. Drift gillnet fisheries for swordfish 

and sharks exist along the entire Pacific coast of Baja California, Mexico and may take animals from this 

population. Quantitative data are available only for the Mexican swordfish drift gillnet fishery, which uses 

vessels, gear, and operational procedures similar to those in the U.S. drift gillnet fishery, although nets may 

be up to 4.5 km long (Holts and Sosa-Nishizaki 1998). The fleet increased from two vessels in 1986 to 31 

vessels in 1993 (Holts and Sosa-Nishizaki 1998). The total number of sets in this fishery in 1992 can be 

estimated from data provided by these authors to be approximately 2700, with an observed rate of marine 

mammal bycatch of 0.13 animals per set (10 marine mammals in 77 observed sets; Sosa-Nishizaki et al. 

1993). This overall mortality rate is similar to that observed in California driftnet fisheries during 1990-95 

(0.14 marine mammals per set; Julian and Beeson, 1998), but species-specific information is not available 

for the Mexican fisheries. Previous efforts to convert the Mexican swordfish driftnet fishery to a longline 

fishery have resulted in a mixed-fishery, with 20 vessels alternately using longlines or driftnets, 23 using 

driftnets only, 22 using longlines only, and seven with unknown gear type (Berdegué 2002). The number 

of set-gillnet vessels in this part of Mexico is unknown. The take of northern elephant seals in other North 

Pacific fisheries that have been monitored appears to be trivial (Barlow et al. 1993, 1994). 

Other Mortality

 Stranding databases for California, Oregon, and Washington states that are maintained by the 

National Marine Fisheries Service contain the following records of human-related elephant seal mortalities 

and injuries in 2000-2004: (1) boat collision (three mortalities), (2) power plant entrainment (1 mortality), 

31
(3) shootings (four mortalities) and (4) entanglement in marine debris (10 injuries). This results in a 

minimum annual average of 1.6 non-fishery related mortalities for 2000-2004.

STATUS OF STOCK

 A generalized logistic growth model of pup counts indicated that the population reached its 

Maximum Net Productivity Level (MNPL) of 19,000 pups in 1992, but has not reached carrying capacity 

(K) at 38,200 pups per year (z = 1, Rmax

= 0.117, n0 = 1,000, SE = 3,376, AICc 

= 500.3) (Figure 3). They are not listed 

as "endangered" or "threatened" under 

the Endangered Species Act nor as 

"depleted" under the MMPA. Because 

their annual human-caused mortality is 

much less than the calculated PBR for 

this stock (4,382), they would not be 

considered a "strategic" stock under the 

MMPA. The average rate of incidental 

fishery mortality for this stock over the 

last five years (>8.8) also appears to be 

less than 10% of the calculated PBR; 

therefore, the total fishery mortality 

appears to be insignificant and 

approaching a zero mortality and 

serious injury rate. This annual rate of 

fishery mortality is negatively biased 

because it excludes mortalities that 

likely occur in the unobserved set 

gillnet fishery for halibut and angel 

shark, where average annual mortality was estimated at approximately 60 animals annually during the 

period 1996-2000. The population is continuing to grow and fishery mortality is relatively constant. 

There are no known habitat issues that are of particular concern for this stock. 

1960 1970 1980 1990 2000

0 10000 20000 30000 40000 50000

Year

Abundance

1992

K = 3.8e+04

MNPL = 1.9e+04

Figure 3. Generalized logistic growth model of elephant 

seal pup counts, 1958-2005. 

REFERENCES

Barlow, J., R. W. Baird, J. E. Heyning, K. Wynne, A. M. Manville, II, L. F. Lowry, D. Hanan, J. Sease, and 

V. N. Burkanov. 1994. A review of cetacean and pinniped mortality in coastal fisheries along the 

west coast of the U.S. and Canada and the east coast of the Russian Federation. Rep. Int. Whal. 

Commn, Special Issue 15:405-425. 

Barlow, J., P. Boveng, M. S. Lowry, B. S. Stewart, B. J. Le Boeuf, W. J. Sydeman, R. J. Jameson, S. G. 

Allen, and C. W. Oliver. 1993. Status of the northern elephant seal population along the U.S. 

west coast in 1992. Admin. Rept. LJ_93_01. Southwest Fisheries Science Center, National 

Marine Fisheries Service, P.O. Box 271, La Jolla, CA. 32 pp. 

Boveng, P. 1988. Status of the northern elephant seal population on the U.S. West Coast. Admin. Rep. 

LJ-88-05 Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, 

La Jolla, CA. 35pp. 

Carretta, J.V. and S.J. Chivers. 2004. Preliminary estimates of marine mammal mortality and biological 

sampling of cetaceans in California gillnet fisheries for 2003. Paper SC/56/SM1 presented to the 

IWC Scientific Committee, June 2004 (unpublished). [Available from Southwest Fisheries 

Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 

92037, USA]. 

Carretta, J.V., S.J. Chivers, and K. Danil. 2005a. Preliminary estimates of marine mammal bycatch, 

mortality, and biological sampling of cetaceans in California gillnet fisheries for 2004. 

Administrative Report LJ-05-10, available from Southwest Fisheries Science Center, 8604 La 

Jolla Shores Drive, La Jolla, California, 92037. 17 p. 

Carretta, J.V., T. Price, D. Petersen, and R. Read. 2005b. Estimates of marine mammal, sea turtle, and 

seabird mortality in the California drift gillnet fishery for swordfish and thresher shark, 1996-

2002. Marine Fisheries Review 66(2):21-30. 

32
Cooper, C. F. and B. S. Stewart. 1983. Demography of northern elephant seals, 1911-1982. Science 

219:969-971. 

Huber, H. R., A. C. Rovetta, L. A. Fry, and S. Johnston. 1991. Age-specific natality of northern elephant 

seals at the South Farallon Islands, California. J. Mamm. 72(3):525-534. 

Le Boeuf, B. J. 1996. Northern elephant seals at Año Nuevo during the breeding seasons of 1992-1996. 

Admin. Rep. LJ-96-12C. Southwest Fisheries Science Center, National Marine Fisheries Service, 

P. O. Box 271, La Jolla, California, 92038. 8 pp. 

Le Boeuf, B. J., D. Crocker, S. Blackwell, and P. Morris. 1993. Sex differences in diving and foraging 

behaviour of northern elephant seals. In: I. Boyd (ed.). Marine Mammal: Advances in 

Behavioural and Population Biology. Oxford Univ. Press. 

Lowry, M. S. 2002. Counts of northern elephant seals at rookeries in the southern California Bight: 1981-

2001. NOAA Technical Memorandum NMFS, NOAA-TM-NMFS-SWFSC-345. Available at 

Southwest Fisheries Science Center, 8604 La Jolla Shores Drive, La Jolla, CA 92037 or at 

http://swfsc.noaa.gov/textblock.aspx?Division=PRD&ParentMenuId=148&id=1253#TechMemos. 

Lowry, M. S., W. L. Perryman, M. S. Lynn, R. L. Westlake, and F. Julian. 1996. Counts of northern 

elephant seals, Mirounga angustirostris, from large-format aerial photographs taken at rookeries in 

southern California during the breeding season. Fish. Bull. 94:176-185. 

McCann, T. S. 1985. Size, status and demography of southern elephant seal (Mirounga leonina) 

populations. In J. K. Ling and M. M. Bryden (eds.), Studies of Sea Mammals in South Latitudes. 

South Australian Museum. 132 pp. 

Perez, M. 2003. Compilation of marine mammal incidental take data from the domestic and joint venture 

groundfish fisheries in the U.S. EEZ of the North Pacific, 1989-2001. U.S. Dep. Commer., 

NOAA Tech. Memo. NMFS-AFSC-138. 145 pp.Sosa-Nishizaki, O., R. De la Rosa Pacheco, R. 

Castro Longoria, M. Grijalva Chon, and J. De la Rosa Velez. 1993. Estudio biologico pesquero 

del pez (Xiphias gladius) y otras especies de picudos (marlins y pez vela). Rep. Int. CICESE, 

CTECT9306. 

Stewart, B. S., and H. R. Huber. 1993. Mirounga angustirostris. Mammalian Species 449:1-10. 

Stewart, B. S., B. J. Le Boeuf, P. K. Yochem, H. R. Huber, R. L. DeLong, R. J. Jameson, W. Sydeman, 

and S. G. Allen. 1994. History and present status of the northern elephant seal population. In: B. 

J. Le Boeuf and R. M. Laws (eds.) Elephant Seals. Univ. Calif. Press, Los Angeles. 

Wade P. R. and R. P. Angliss. 1997. Guidelines for assessing marine mammal stocks: Report of the 

GAMMS Workshop April 3-5, 1996, Seattle, Washington. NOAA Technical Memorandum 

NMFS-OPR-12 available from Office of Protected Resources, National Marine Fisheries Service, 

Silver Springs, MD. 93pp. 

33
Revised 12/15/2000

GUADALUPE FUR SEAL (Arctocephalus townsendi) 

STOCK DEFINITION AND GEOGRAPHIC

RANGE

Commercial sealing during the 19th 

century reduced the once abundant Guadalupe fur 

seal to near extinction in 1894 (Townsend 1931). 

Prior to the harvest it ranged from Monterey Bay,

California, to the Revillagigedo Islands, Mexico

(Fleischer 1987, Hanni et al. 1997; Figure 1). The

capture of two adult males at Guadalupe Island in 

1928 established the specie’s continued existence 

(Townsend 1931); however, they were not seen 

again until 1954 (Hubbs 1956). Guadalupe fur 

seals pup and breed mainly at Isla Guadalupe, 

Mexico. In 1997, a second rookery was

discovered at Isla Benito del Este, Baja California 

(Maravilla-Chavez and Lowry 1999) and a pup 

was born at San Miguel Island, California (Melin

and DeLong 1999). Individuals have stranded or

been sighted as far north as Blind Beach, 

California (38o 26' 10" N, 123o 07' 20" W); inside

the Gulf of California and as far south as

Zihuatanejo, Mexico (17o 39' N, 101o 34'W; Hanni

et al. 1997 and Aurioles-Gamboa and HernadezCamacho 1999). The population is considered to

be a single stock because all are recent descendants 

from one breeding colony at Isla Guadalupe,

Mexico. 

W130 W125 W120 W115 W110 W105 W100

Longitude

N15

N20

N25

N30

N35

N40

N45

Latitude

WASHINGTON

OREGON

CALIFORNIA

MEXICO

UNITED STATES

PACIFIC OCEAN

Isla Guadalupe

Isla Benito

 Del Este

 Islas

Revillagigedos

Figure 1. Geographic range of the Guadalupe fur 

seal, showing location of two rookeries at Isla

Guadalupe and Isla Benito Del Este.

POPULATION SIZE

The size of the population prior to the commercial harvests of the 19th century is not known, but

estimates range from 20,000 to 100,000 animals (Wedgeforth 1928, Hubbs 1956, Fleischer 1987). The

population was estimated by Gallo (1994) to be about 7,408 animals in 1993. The population estimate was 

derived by multiplying the number of pups (counted and estimated) by a factor of 4.0. 

Minimum Population Estimate

All the individuals of the population cannot be counted because all age and sex classes are never 

ashore at the same time and some individuals that are on land are not visible during the census. Subsampling portions of the rookery indicate that only 47-55% of the seals present (i.e., hauled out) are

counted during the census (Gallo 1994). The 1993 count of all age classes plus the estimate of missed

animals was 6,443 (Gallo 1994). The minimum size of the population in Mexico can be estimated as the 

actual count of 3,028 hauled out seals [The actual count data were not reported by Gallo (1994); this

number is derived by multiplying the estimated number hauled out by 47%, the minimum estimate of the 

percent counted]. In the United States, a few Guadalupe fur seals are known to inhabit California sea lion

rookeries in the Channel Islands (Stewart et al. 1987). 

Current Population Trend

Counts of Guadalupe fur seals have been made sporadically since 1954. Records of Guadalupe fur 

seal counts through 1984 were compiled by Seagars (1984), Fleischer (1987), and Gallo (1994). The count 

for 1988 was taken from Torres et al. (1990). A few of these counts were made during the breeding season, 

but the majority were made at other times of the year (Figure 1). Also, the counts that are documented in 

the literature generally provide only the total of all Guadalupe fur seals counted (i.e., the counts are not

separated by age/sex class). The counts that were made during the breeding season, when the maximum

34
number of animals are present at the 

rookery, were used to examine

population growth (Gallo 1994). The 

natural logarithm of the counts was 

regressed against year to calculate the 

growth rate of the population. These 

data indicate that the population of

Guadalupe fur seals is increasing

exponentially at an average annual 

growth rate of 13.7% (Gallo 1994; 

Figure 2).

CURRENT AND MAXIMUM NET 

PRODUCTIVITY RATES

The maximum net productivity 

rate can be assumed to be equal to the

annual growth rate observed over the

last 30 years (13.7%) because the

population was at a very low level and

should have been growing at nearly its

maximum rate.

0 

1000 

2000 

3000 

4000 

5000 

6000 

7000 

COUNTS

50 55 60 65 70 75 80 85 90 95

YEAR

Non-breeding season Breeding season Pop. growth curve

GUADALUPE FUR SEAL COUNTS

Guadalupe Island, Mexico

Figure 2. Counts of Guadalupe fur seals at Guadalupe 

Island, Mexico, and the estimated population growth curve 

derived from counts made during the breeding season. POTENTIAL BIOLOGICAL 

REMOVAL

The potential biological removal (PBR) for this stock is calculated as the minimum population 

size (3,028) times one half the default maximum net growth rate for pinnipeds (1⁄2 of 12%) times a recovery 

factor of 0.5 (for a threatened species, Wade and Angliss 1997), resulting in a PBR of 91 Guadalupe fur

seals per year. The vast majority of this PBR would apply towards incidental mortality in Mexico. 

HUMAN-CAUSED MORTALITYAND SERIOUS INJURY

Fisheries Information

Drift and set gillnet fisheries may cause incidental mortality of Guadalupe fur seals in Mexico and 

the United States. In the United States there have been no reports of mortalities or injuries for Guadalupe

fur seals (Barlow et al.1994, Julian 1997, Julian and Beeson 1998, Cameron and Forney 1999. No

information is available for human-caused mortalities or injuries in Mexico. However, similar drift gillnet 

fisheries for swordfish and sharks exist along the entire Pacific coast of Baja California, Mexico and may 

take animals from the same population. Quantitative data are available only for the Mexican swordfish 

drift gillnet fishery (Sosa-Nishizaki et al. 1993). The total number of sets in this fishery in 1992 can be

estimated from data provided by these authors to be approximately 2,700, with an observed rate of marine

mammal bycatch of 0.13 animals per set (10 marine mammals in 77 observed sets; Sosa-Nishizaki et al. 

1993). This overall mortality rate is similar to that observed in California driftnet fisheries during 1990-93 

(0.15 marine mammals per set), but species-specific information is not available for the Mexican fisheries. 

There are currently efforts underway to convert the Mexican swordfish driftnet fishery to a longline fishery 

(D. Holts, pers. comm.). The number of set gillnets used in Mexico is unknown.

Other mortality

Juvenile female Guadalupe fur seals have stranded in central and northern California with net abrasions

around the neck, fish hooks and monofilament line, and polyfilament string (Hanni et al. 1997).

STATUS OF STOCK

The state of California lists the Guadalupe fur seal as a fully protected mammal in the Fish and 

Game Code of California (Chap. 8, sec. 4700, d), and it is listed also as a threatened species in the Fish and 

Game Commission California Code of Regulations (Title 14, sec. 670.5, b, 6, H). The Endangered Species 

Act lists it as a threatened species, which automatically qualifies this as a "depleted" and "strategic" stock

under the Marine Mammal Protection Act. There is insufficient information to determine whether the 

fishery mortality in Mexico exceeds the PBR for this stock. The total U.S. fishery mortality and serious 

35
injury for this stock is less than 10% of the calculated PBR and, therefore, can be considered to be 

insignificant and approaching zero mortality and serious injury rate. The population is growing at 

approximately 13.7% per year.

Table 1. Summary of available information on the incidental mortality and injury of Guadalupe fur seals in 

commercial fisheries that might take this species (Julian 1997, Julian and Beeson 1998, Cameron and 

Forney 1999, M. Perez per. comm, Appendix 1). Mean annual takes are based on 1994-98 data unless 

noted otherwise.

Fishery Name Year(s) Data Type

Percent 

Observer 

Coverage

Observed

Mortality

Estimated 

Mortality (CV in 

parentheses)

Mean 

Annual Takes 

(CV in parentheses)

CA driftnet fishery for 

sharks and swordfish

1994 

1995 

1996 

1997 

1998 

observer 

17.9% 

15.6% 

12.4% 

22.8% 

20.2% 

0 

0 

0 

0

0

0 

0 

0 

0

0

01

CA set gillnet fishery 

for halibut and angel 

shark

1994 

1995 

1996 

1997

1998

observer 

extrapolated 

estimates 

(1995-98)

7.7% 

0% 

0% 

0%

0%

0 

0 

0 

0

0

0 

02

02

02

02

02

WA, OR, CA ground 

fish trawl fishery (Atsea processing Pacific 

whiting fishery only)

1994 

1995 

1996 

1997

1998

observer 

53.8% 

56.2% 

65.2% 

65.7%

77.3%

0 

0 

0 

0

0

0 

0 

0 

0

0

0

Minimum total annual takes 0

1

 Only 1997-98 mortality estimates are included in the average because of gear modifications implemented within the fishery as part 

of a 1997 Take Reduction Plan. Gear modifications included the use of net extenders and acoustic warning devices (pingers). 2

 The CA set gillnets were not observed after 1994; mortality was extrapolated from effort estimates and previous entanglement rates. 

REFERENCES

Aurioles-Gamboa, D. and C. J. Hernadez-Camacho. 1999. Notes on the southernmost records of 

Guadalupe fur seal, Arctocephalus townsendi, in Mexico. Mar. Mamm. Sci. 15:581-583. 

Barlow, J., R. W. Baird, J. E. Heyning, K. Wynne, A. M. Manville II, L. F. Lowry, D. Hanan, J. Sease, and 

V. N. Burkanov. 1994. A review of cetacean and pinniped mortality in coastal fisheries along the 

west coast of the USA and Canada and the east coast of the Russian Federation. Rept. Int. 

Whaling Comm., Special Issue 15:405-425. 

Cameron, G., and K. A. Forney. 1999. Estimates of cetacean mortality in the California gillnet fisheries for 

1997 and 1998. Paper SC/51/O4 presented to the International Whaling Commission, May 1999 

(unpublished). 14 pp. 

Fleischer, L. A. 1987. Guadalupe fur seal, Arctocephalus townsendi. In J. P. Croxall and R. L. Gentry 

(eds.). Status, biology, and ecology of fur seals. Proceedings of an international symposium and 

workshop. Cambridge, England, 23-27 April 1984. p. 43-48. U.S. Dept. of Commerce, NOAA, 

NMFS, NOAA Tech. Rept. NMFS 51. 

Gallo, J. P. 1994. Factors affecting the population status of Guadalupe fur seal, Arctocephalus townsendi

(Merriam, 1897), at Isla de Guadalupe, Baja California, Mexico. Ph.D. Thesis, University of 

California, Santa Cruz, 199 p. 

Hanni, K. D., D. J. Long, R. E. Jones, P. Pyle, and L. E. Morgan. 1997. Sightings and strandings of 

Guadalupe fur seals in central and northern California, 1988-1995. J. of Mamm. 78:684-690. 

Holts, D. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La Jolla, 

CA 92038. 

Hubbs. C. L. 1956. The Guadalupe fur seal still lives! Zoonooz, S. D. Zool. Soc. 29(12):6-9. 

36
Julian, F. 1997. Cetacean mortality in California gill net fisheries: Preliminary estimates for 1996. Paper 

SC/49/SM02 presented to the International Whaling Commission, September 1997 (unpublished). 

13 pp. 

Julian, F. and M. Beeson. 1998. Estimates for marine mammal, turtle, and seabird mortality for two 

California gillnet fisheries: 1990-95. Fish. Bull. 96:271-284. 

Maravilla-Chavez, M. O. and M. S Lowry. 1999 Incipient breeding colony of Guadalupe fur seals at Isla 

Benito del 

 Este, Baja California, Mexico. Mar. Mamm. Sci. 15:239-241. 

Melin, S. R. and R. L. DeLong. 1999. Observations of a Guadalupe fur seal (Arctocephalus townsendi) 

female and pup at San Miguel Island, California. Mar. Mamm. Sci. 15:885-888. 

Perkins, P., J. Barlow, and M. Beeson. 1992. Pinniped and cetacean mortality in California gillnet 

fisheries: 1991. Rept. Int. Whaling Commission, Working Paper SC/44/SM14. 

Seagars, D. J. 1984. The Guadalupe fur seal: a status review. National Marine Fisheries Service, 

Southwest Region, Admin. Rep. SWR-84-6. 29pp. 

Sosa-Nishizaki, O., R. De la Rosa Pacheco, R. Castro Longoria, M. Grijalva Chon, and J. De la Rosa 

Velez. 1993. Estudio biologico pesquero del pez (Xiphias gladius) y otras especies de picudos 

(marlins y pez vela). Rep. Int. CICESE, CTECT9306. 

Stewart, B. S., P. K. Yochem, R. L. DeLong, and G.A. Antonelis Jr. 1987. Interactions between 

Guadalupe fur seals and California sea lions ant San Nicolas and San Miguel islands, California. 

In J. P. Croxall and R. L. Gentry (eds.). Status, biology, and ecology of fur seals. Proceedings of 

an international symposium and workshop. Cambridge, England, 23-27 April 1984. p. 103-106. 

U.S. Dept. of Commerce, NOAA, NMFS, NOAA Tech. Rept. NMFS 51. 

Torres-G., A., A. Aguayo-L., and N. Valdez-T. 1990. Tamaño y distribucion de la poblacion del lobo fino 

de Guadalupe, Arctocephalus townsendi (Merriam, 1897), durante el verano de 1988. [Abstracts] 

XV Reunion internacional para el estudio de los mamiferos marinos, 18-20 April 1990. La Paz, B. 

C. S., Mexico. 

Townsend, C. H. 1931. The fur seal of the California islands with new descriptive and historical matter. 

Zoologica 9:443-457. 

Wedgeforth, H. M. 1928. The Guadalupe fur seal (Arctocephalus townsendi). Zoonooz, S. D. Zool. Soc. 

3(3):4-9. 

37
Revised 12/15/2006

NORTHERN FUR SEAL (Callorhinus ursinus): San Miguel Island Stock

STOCK DEFINITION AND GEOGRAPHIC RANGE

Northern fur seals occur from southern

California north to the Bering Sea and west to the 

Okhotsk Sea and Honshu Island, Japan (Fig. 1). During

the breeding season, approximately 74% of the 

worldwide population is found on the Pribilof Islands in 

the southern Bering Sea, with the remaining animals

spread throughout the North Pacific Ocean (Lander and 

Kajimura 1982). Of the seals in U.S. waters outside of 

the Pribilofs, approximately 1% of the population is 

found on Bogoslof Island in the southern Bering Sea and

San Miguel Island off southern California (NMFS

1993). Northern fur seals may temporarily haul out on

land at other sites in Alaska, British Columbia, and on

islets along the coast of the continental United States,

but generally this occurs outside of the breeding season

(Fiscus 1983).

Due to differing requirements during the annual 

reproductive season, adult males and females typically

occur ashore at different, though overlapping, times.

Adult males usually occur on shore during the 4-month

period from May-August, though some may be present

until November (well after giving up their territories).

Adult females are found ashore for as long as six months 

(June-November). After their respective times ashore,

seals of both genders spend the next 7-8 months at sea

(Roppel 1984). Adult females and pups from the Pribilof 

Islands migrate through the Aleutian Islands into the 

North Pacific Ocean, often to Oregon and California offshore waters. Many pups may remain at sea for 22 months

before returning to their rookery of birth. Adult males from the Pribilof Islands generally migrate only as far south

as the Gulf of Alaska (Kajimura 1984). There is considerable interchange of individuals between rookeries. 

San Miguel Island

Pribilof

Islands

Figure 1. Approximate distribution of northern fur

seals in the eastern North Pacific (shaded area). 

The following information was considered in classifying stock structure based on the Dizon et al. (1992) 

phylogeographic approach: 1) Distributional data: continuous geographic distribution during feeding, geographic

separation during the breeding season, and high natal site fidelity (DeLong 1982); 2) Population response data:

substantial differences in population dynamics between the Pribilofs and San Miguel Island (DeLong 1982, DeLong

and Antonelis 1991, NMFS 1993); 3) Phenotypic data: unknown; and 4) Genotypic data: unknown. Based on this 

information, two separate stocks of northern fur seals are recognized within U.S. waters: an Eastern Pacific stock

and a San Miguel Island stock. The Eastern Pacific stock is reported separately in the Stock Assessment Reports for 

the Alaska Region. 

POPULATION SIZE

The population estimate for the San Miguel Island stock of northern fur seals is calculated as the estimated 

number of pups at rookeries multiplied by an expansion factor. Based on research conducted on the Eastern Pacific

stock of northern fur seals, Lander’s (1981) life table analysis was used to estimate the number of yearlings, twoyear-olds, three-year-olds, and animals at least four years old. The resulting population estimate was equal to the 

pup count multiplied by 4.475. The expansion factors are based on a sex and age distribution estimated after the 

commercial harvest of juvenile males was terminated in 1984. A more appropriate expansion factor for the San 

Miguel Island stock is 4.0, based on the known increased immigration of recruitment-age females (DeLong 1982)

and mortality and possible emigration of adults associated with the El Niño Southern Oscillation events in 1982-

1983 and 1997-1998 (R. DeLong, pers. comm.). A 1998 pup count resulted in an 80% decrease from the 1997 count

(Melin et al. 2005). In 1999, the population began to recover, and by 2005 the total pup count was 2,356 (S. Melin, 

unpubl. data). Based on the 2005 count and the expansion factor, the most recent population estimate of the San

38
Miguel Island stock is 9,424 (2,356 x 4.0) northern fur seals. Currently, a CV for the expansion factor is

unavailable. 

Minimum Population Estimate

The survey technique utilized for estimating the abundance of northern fur seals within the San Miguel

Island stock is a direct count, with no associated coefficient of variation (CV), as sites are surveyed only once. 

Additional estimates of the overall population size (i.e., NBEST) and associated CV are also unavailable. Therefore, 

the minimum population size for this stock cannot be estimated by calculating the lower 20th percentile of the lognormal distribution of the population estimate. Rather, the minimum population size is estimated as twice the 

maximum number of pups born in 2005 (to account for the pups and their mothers) plus the maximum number of

adult and sub-adult males counted for the 2005 season, which results in an estimate of 5,096 ((2,356 x 2) + 384). 

This method provides a very conservative estimate of the northern fur seal population at San Miguel Island. 

Current Population Trend

The population of northern fur

seals on San Miguel Island originated from

the Pribilof Islands population during the

late 1950s or early 1960s (DeLong 1982). 

The colony has increased steadily, since its 

discovery in 1968, except for severe 

declines in 1983 and 1998 associated with

El Niño Southern Oscillation events in 

1982-1983 and 1997-1998 (DeLong and 

Antonelis 1991, Melin et al. 2005). El Niño 

events, which occur periodically along the

California coast, impact population growth

of northern fur seals at San Miguel Island

and are an important regulatory mechanism 

for this population (DeLong and Antonelis 

1991; Melin and DeLong 1994, 2000;

Melin et al. 1996, 2005). 

Specifically, live pup counts

increased about 24% annually from 1972

through 1982, an increase due, in part, to

immigration of females from the Bering

Sea and the western North Pacific Ocean 

(DeLong 1982). The 1982-1983 El Niño 

event resulted in a 60.3% decline in the 

northern fur seal population at San Miguel

Island (DeLong and Antonelis 1991). It took the population 7 years to recover from this decline, because adult

female mortality occurred in addition to pup mortality (Melin and DeLong 1994). The 1992-1993 El Niño

conditions resulted in reduced pup production in 1992, but the population recovered in 1993 and increased in 1994 

(Melin et al. 1996). 

0

500

1000

1500

2000

2500

3000

3500

1970 1975 1980 1985 1990 1995 2000 2005 2010

Year

Estimated Production

Figure 2. Northern fur seal estimated production on San Miguel

Island, 1972-2005. 

From July 1997 through May 1998, the most severe El Niño event in recorded history affected California 

coastal waters (Lynn et al. 1998). In 1997, total fur seal pup production was the highest recorded since the colony

has been monitored (Fig. 2). However, it appears that up to 87% of the pups born in 1997 died before weaning, and

total production in 1998 declined 80% from 1997 (Melin et al. 2005). Although total production increased to 2,356 

in 2005 (S. Melin, unpubl. data), the population has not yet recovered. Recovery from the 1998 decline has been

slowed by the adult female mortality which occurred in addition to the high pup mortality in 1997 and 1998 (Melin 

et al. 2005; S. Melin, unpubl. data). 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

The northern fur seal population in the Pribilof Islands increased steadily during 1912-1924 after the 

commercial harvest no longer included pregnant females. During this period, the rate of population growth was 

approximately 8.6% (SE=1.47) per year (A. York, unpubl. data), the maximum recorded for this species. This 

growth rate is similar to and slightly higher than the 8.12% rate of increase (approximate SE=1.29) estimated by

39
Gerrodette et al. (1985). Given the extremely low density of the population in the early 1900s, the 8.6% rate of 

increase is considered a reliable estimate of RMAX. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population 

estimate (5,096) times one-half the observed maximum net growth rate (1⁄2 of 8.6%) times a recovery factor of 1.0 

(for stocks of unknown status that are increasing in size: Wade and Angliss 1997), resulting in a PBR of 219 San 

Miguel Island northern fur seals per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fisheries Information

 Northern fur seals taken during the winter/spring along the west coast of the continental U.S. could be from 

the Pribilofs and, thus, belong to the Eastern Pacific stock. However, it is the intention of NMFS to consider any 

takes of northern fur seals by commercial fisheries in waters off California, Oregon, and Washington as being from 

the San Miguel Island stock. Information concerning the three observed fisheries that may have interacted with 

northern fur seals is listed in Table 1. There were no observer reports of northern fur seal mortalities in any 

observed fishery along the west coast of the continental U.S. in 2000-2004 (Table 1; Perez 2003; Carretta and 

Chivers 2004; Carretta et al. 2005a, 2005b; J. Cusick, unpubl. data). The estimated mean mortality rate in observed 

fisheries is zero northern fur seals per year from this stock. 

 The Marine Mammal Authorization Program (MMAP) fisher self-reports, required of commercial vessel 

operators by the MMPA, are an additional source of information on the number of northern fur seals killed or 

seriously injured incidental to commercial fishery operations. Between 2000 and 2004, there were no fisher selfreports of northern fur seal mortalities in any MMAP-listed fishery operating in waters off California, Oregon, or 

Washington. Although these reports are considered incomplete (see details in Appendix 1), they represent a 

minimum mortality. 

 Strandings of northern fur seals entangled in fishing gear or with serious injuries caused by interactions 

with gear are a final source of fishery-related mortality information. According to Marine Mammal Stranding 

Network records, maintained for California by the NMFS Southwest Region and for Oregon and Washington by the 

NMFS Northwest Region, fishery-related strandings were reported in 2001 (1 in California and 1 in Oregon) and 

2003 (3 in Oregon). Since these mortalities could not be attributed to a particular fishery, they are listed in Table 1 

as occurring in an unknown west coast fishery. Fishery-related strandings during 2000-2004 resulted in an 

estimated annual mortality of 1.0 animal from this stock. This estimate is considered a minimum because not all 

stranded animals are found, reported, or examined for cause of death (via necropsy by trained personnel). 

Other Mortality

 According to the Marine Mammal Stranding Network records, maintained by the NMFS Southwest and 

Northwest Regions, no human-caused northern fur seal mortalities were reported from non-fisheries sources in 

2000-2004. This estimate is considered a minimum because not all stranded animals are found, reported, or 

examined for cause of death (via necropsy by trained personnel). 

STATUS OF STOCK

 The San Miguel Island northern fur seal stock is not considered to be “depleted” under the MMPA or listed 

as “threatened” or “endangered” under the Endangered Species Act. Based on currently available data, the 

estimated annual level of total human-caused mortality and serious injury (1.0) does not exceed the PBR (219). 

Therefore, the San Miguel Island stock of northern fur seals is not classified as a “strategic” stock. The minimum 

total fishery mortality and serious injury for this stock (1.0) is not known to exceed 10% of the calculated PBR 

(21.9) and, therefore, appears to be insignificant and approaching zero mortality and serious injury rate. The stock 

decreased 80% from 1997 to 1998, began to recover in 1999, and is currently at 74% of the 1997 level. The status 

of this stock relative to its Optimum Sustainable Population (OSP) level is unknown, unlike the Eastern Pacific 

northern fur seal stock which is formally listed as “depleted” under the MMPA. 

40
Table 1. Summary of available information on the incidental mortality and serious injury of northern fur seals (San 

Miguel Island stock) in commercial fisheries that might take this species and calculation of the mean annual 

mortality rate; n/a indicates that data are not available. Mean annual takes are based on 2000-2004 data unless noted 

otherwise. 

Fishery name Years Data type

Percent 

observer 

coverage

Observed

mortality

Estimated

mortality

Mean annual takes 

(CV in 

parentheses)

CA/OR thresher shark/ 

swordfish drift gillnet

2000 

2001 

2002 

2003 

2004 

observer

22.9% 

20.4% 

22.1% 

20.2% 

20.6% 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0

CA angel shark/halibut and 

other species large mesh (>3.5 

in) set gillnet

2000 

2001 

2002 

2003 

2004 

No fisherywide 

observer 

program 

since 1994

1.8%1 

0% 

0% 

0% 

0% 

0 

n/a 

n/a 

n/a 

n/a 

0 

n/a 

n/a 

n/a 

n/a 

0

WA/OR/CA groundfish trawl 

(Pacific hake at-sea processing 

component)

2000 

2001 

2002 

2003 

2004

observer

80.6%2 

96.2%2 

100%3 

100%3 

100%3 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0

WA/OR/CA groundfish trawl 

(Pacific hake at-sea processing 

component)

2000-2004

MMAP 

self-reports

n/a 0, 0, 0, 0, 0 n/a 0

Unknown west coast fishery 2000-2004 stranding n/a 0, 2, 0, 3, 0 n/a ≥1.0 (n/a) 

Minimum total annual takes ≥1.0 (n/a) 

1

In 2000, approximately 25% of the Monterey Bay portion of the set gillnet fishery was observed, representing <5% of the overall fishery. There 

has been no observer program for this fishery since 2000. 

2

Percent observer coverage equals percent of observed catch; observers were present on 100% of the vessels. 3

Percent observer coverage equals percent of vessels with observers. 

REFERENCES

Carretta, J. V., and S. J. Chivers. 2004. Preliminary estimates of marine mammal mortality and biological sampling 

of cetaceans in California gillnet fisheries for 2003. Paper SC/56/SM1 presented to the International 

Whaling Commission, July 2004 (unpublished). 18 pp. Available from Southwest Fisheries Science 

Center, 8604 La Jolla Shores Drive, La Jolla, CA 92037. 

Carretta, J. V., S. J. Chivers, and K. Danil. 2005a. Preliminary estimates of marine mammal bycatch, mortality, and 

biological sampling of cetaceans in California gillnet fisheries for 2004. Administrative Report LJ-05-10. 

17 pp. Available from Southwest Fisheries Science Center, 8604 La Jolla Shores Drive, La Jolla, CA 

92037. 

Carretta, J. V., T. Price, D. Petersen, and R. Read. 2005b. Estimates of marine mammal, sea turtle, and seabird 

mortality in the California drift gillnet fishery for swordfish and thresher shark, 1996–2002. Mar. Fish. 

Rev. 66(2):21-30. 

Cusick, J. West Coast Groundfish Observer Program, Fishery Resource Analysis and Monitoring Division, 

NWFSC, NMFS, 2725 Montlake Blvd. E, Seattle, WA 98112. 

DeLong, R. L. National Marine Mammal Laboratory, AFSC, NMFS, 7600 Sand Point Way NE, Seattle, WA 

98115. 

DeLong, R. L. 1982. Population biology of northern fur seals at San Miguel Island, California. Ph.D. Thesis, 

University of California, Berkeley, California. 185 pp. 

DeLong, R. L., and G. A. Antonelis. 1991. Impacts of the 1982-1983 El Niño on the northern fur seal population at 

San Miguel Island, California. Pp. 75-83, In: Trillmich, F., and K. Ono (eds.), Pinnipeds and El Niño: 

Responses to Environmental Stress. Springer-Verlag, New York. 293 pp. 

Dizon, A. E., C. Lockyer, W. F. Perrin, D. P. DeMaster, and J. Sisson. 1992. Rethinking the stock concept: a 

phylogeographic approach. Conserv. Biol. 6:24-36. 

41
Fiscus, C. H. 1983. Fur seals and islands. In: Background papers submitted by the United States to the 26th 

meeting of the Standing Scientific Committee of the North Pacific Fur Seal Commission, Washington, 

D.C., March 28-April 5, 1983. Available at National Marine Mammal Laboratory, 7600 Sand Point Way 

NE, Seattle, WA 98115. 

Gerrodette, T., D. Goodman, and J. Barlow. 1985. Confidence limits for population projections when vital rates 

vary randomly. Fish. Bull. 83(3):207-217. 

Kajimura, H. 1984. Opportunistic feeding of the northern fur seal, Callorhinus ursinus, in the eastern North Pacific 

Ocean and eastern Bering Sea. NOAA Tech. Rep. NMFS-SSRF-779. 49 pp. 

Lander, R. H. 1981. A life table and biomass estimate for Alaskan fur seals. Fisheries Research (Amsterdam) 1:55-

70. 

Lander, R. H., and H. Kajimura. 1982. Status of northern fur seals. FAO Fisheries Series 5:319-345. 

Lynn, R. J., T. Baumgartner, J. Garcia, C. A. Collins, T. L. Hayward, K. D. Hyrenbach, A. W. Mantyla, T. 

Murphree, A. Shankle, F. B. Schwing, K. M. Sakuma, and M. J. Tegner. 1998. The state of the California 

Current, 1997-1998: transition to El Niño conditions. CalCOFI Report 39:25-49. 

Melin, S. R. National Marine Mammal Laboratory, AFSC, NMFS, 7600 Sand Point Way NE, Seattle, WA 98115. 

Melin, S. R., and R. L. DeLong. 1994. Population monitoring of northern fur seals on San Miguel Island, 

California. Pp. 137-141, In: Sinclair, E. H. (ed.), Fur seal investigations, 1992. U.S. Dep. Commer., 

NOAA Tech. Memo. NMFS-AFSC-45. 190 pp. 

Melin, S. R., and R. L. DeLong. 2000. Population monitoring studies of northern fur seals at San Miguel Island, 

California. Pp. 41-51, In: Robson, B. W. (ed.), Fur seal investigations, 1998. U.S. Dep. Commer., NOAA 

Tech. Memo. NMFS-AFSC-113. 101 pp. 

Melin, S. R., R. L. DeLong, and J. R. Thomason. 1996. Population monitoring studies of northern fur seals at San 

Miguel Island, California. Pp. 87-102, In: Sinclair, E. H. (ed.), Fur seal investigations, 1994. U.S. Dep. 

Commer., NOAA Tech. Memo. NMFS-AFSC-69. 144 pp. 

Melin, S. R., R. L. DeLong, and A. J. Orr. 2005. The status of the northern fur seal population at San Miguel 

Island, California, 2002-2003. Pp. 44-52, In: Testa, J. W. (ed.), Fur seal investigations, 2002-2003. U.S. 

Dep. Commer., NOAA Tech. Memo. NMFS-AFSC-151. 72 pp. 

National Marine Fisheries Service (NMFS). 1993. Final conservation plan for the northern fur seal (Callorhinus 

ursinus). Prepared by the National Marine Mammal Laboratory, Alaska Fisheries Science Center, NMFS, 

Seattle, WA, and the Office of Protected Resources, NMFS, Silver Spring, MD. 80 pp. 

Perez, M. 2003. Compilation of marine mammal incidental take data from the domestic and joint venture 

groundfish fisheries in the U.S. EEZ of the North Pacific, 1989-2001. U.S. Dep. Commer., NOAA Tech. 

Memo. NMFS-AFSC-138. 145 pp. 

Roppel, A. Y. 1984. Management of northern fur seals on the Pribilof Islands, Alaska, 1786-1981. U.S. Dep. 

Commer., NOAA Tech. Rep. NMFS-4. 32 pp. 

Wade, P. R., and R. Angliss. 1997. Guidelines for assessing marine mammal stocks: report of the GAMMS 

workshop April 3-5, 1996, Seattle, Washington. U.S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

York, A. E. National Marine Mammal Laboratory, AFSC, NMFS, 7600 Sand Point Way NE, Seattle, WA 98115. 

42
Revised 10/30/2007

HAWAIIAN MONK SEAL (Monachus schauinslandi)

STOCK DEFINITION AND GEOGRAPHIC RANGE

Hawaiian monk seals are distributed predominantly in six Northwestern Hawaiian Islands (NWHI) 

subpopulations at French Frigate Shoals, Laysan and Lisianski Islands, Pearl and Hermes Reef, and Midway and 

Kure Atoll. Small numbers also occur at Necker, Nihoa, and the main Hawaiian Islands (MHI). Genetic variation 

among NWHI monk seals is extremely low and may reflect both a long-term history at low population levels and 

more recent human influences (Kretzmann et al. 1997, 2001). On average, 10-15% of the seals migrate among the 

NWHI subpopulations (Johnson and Kridler 1983; Harting 2002). Thus, the NWHI subpopulations are not isolated, 

though the different island subpopulations have exhibited considerable demographic independence. Observed 

interchange of individuals among the NWHI and MHI regions is extremely rare, suggesting these may be more 

appropriately designated as separate stocks. Further evaluation of a separate MHI stock will be pursued following 

genetic stock structure analysis (currently underway) and additional studies of MHI monk seals. In the mean time, 

the species is managed as a single stock. 

POPULATION SIZE

 The best estimate of the total population size is 1,247. This estimate is the sum of estimated abundance at 

the six main Northwest Hawaiian Islands subpopulations, an extrapolation of counts at Necker and Nihoa Islands, 

and an estimate of minimum abundance in the main Hawaiian Islands. The number of individual seals identified 

was used as the population estimate at NWHI sites where total enumeration was achieved according to the criteria 

established by Baker et al. (2006). Where total enumeration was not achieved, capture-recapture estimates from 

Program CAPTURE were used (Baker 2004; Otis et al. 1978, Rexstad & Burnham 1991, White et al. 1982). When 

no reliable estimator was obtainable in Program CAPTURE (i.e., the model selection criterion was < 0.75, following 

Otis et al. 1978), the total number of seals identified was the best available estimate. Finally, sometimes capturerecapture estimates are less than the known minimum abundance (Baker 2004), and in these cases the total number 

of seals identified was used. In 2005, identification efforts were conducted during two- to six-month studies at all 

main reproductive sites. Total enumeration was achieved at Midway Atoll, and capture-recapture estimates were 

obtained at the remaining sites. At Pearl and Hermes Reef and Kure Atoll, this estimate was lower than the known 

minimum abundance, so that the latter was considered the best estimate. The total abundance estimate at the six 

main subpopulations in 2005 was 1,072 seals (including 163 pups) . Monk seals also occur at Necker and Nihoa 

Islands, where counts are conducted from zero to a few times in a single year. Abundance is estimated by correcting 

the mean of all beach counts accrued over the past five years. The mean (±SD) of all counts (excluding pups) 

conducted between 2001 and 2005 was 14.4 (±4.3) at Necker Island and 17.7 (±8.3) at Nihoa Island (Johanos and 

Baker 2004, 2005, in press, in prep.). The relationship between mean counts and total abundance at the reproductive 

sites indicates that the total abundance can be estimated by multiplying the mean count by a correction factor of 2.89 

(NMFS unpubl. data). Resulting estimates (plus the average number of pups known to have been born during 2001-

2005) are 43.3 (±12.5) at Necker Island and 54.9 (±24.0) at Nihoa Island. 

 The only complete and systematic surveys for monk seals in the MHI were conducted in 2000 and 2001 

(Baker and Johanos 2004). The NMFS collects information on seal sightings reported by a variety of sources. 

Recently, the number of such reports has increased and related database improvement efforts have been underway. 

The total number of individually identifiable seals documented in this way in 2005 was 77, the current best 

minimum abundance estimate. 

Minimum Population Estimate

 The total number of seals (1,065) identified at the six main NWHI reproductive sites is the best estimate of 

minimum population size at those sites. Minimum population sizes for Necker and Nihoa Islands (based on the 

formula provided by Wade and Angliss (1997)) are 34 and 39, respectively. The minimum abundance estimate for 

the main Hawaiian Islands in 2005 is 77 seals. The minimum population size for the entire stock (species) is the 

sum of these estimates, or 1,214 seals. 

43
Current Population Trend 

 The total of mean non-pup beach counts at the six main reproductive NWHI subpopulations in 2005 is 67% 

lower than in 1958. The trend in total abundance at the six main NWHI subpopulations estimated as described above 

is shown in Figure 1. A log-linear regression of estimated abundance on year from 1998 (the first year for which a 

reliable total abundance estimate has been obtained) to 2005 estimates that abundance declined -3.8% yr-1 (95% CI 

= -5.0% to -2.6% yr-1). 

CURRENT AND MAXIMUM NET 

PRODUCTIVITY RATES

Figure 1. Trend in abundance of monk seals at the six main 

Northwestern Hawaiian Islands subpopulations, based on a 

combination of total enumeration and capture–recapture 

estimates. Error bars indicate ±2 s.e. (from variances of 

capture-recapture estimates). Fitted log-linear regression line is 

shown. 

Year

1998 2000 2002 2004 2006

Estimated Abundance (± 2 s.e

1000

1100

1200

1300

1400

1500

.)

 Trends in abundance vary 

considerably among the six main 

subpopulations. Mean non-pup beach 

counts are used as a long-term index of 

abundance for years when data are 

insufficient to estimate total abundance 

as described above). Beach counts at 

French Frigate Shoals declined 73% 

from 1989-2005. Populations at Laysan 

and Lisianski Islands have remained 

relatively stable since approximately 

1990, though the former has tended to 

increase slightly while the latter has 

decreased slowly. 

 Until recently, the three 

westernmost subpopulations, Kure, 

Midway and Pearl and Hermes Reef 

exhibited substantial growth. The 

subpopulation at Pearl and Hermes Reef 

increased after the mid-1970s. Prior to 

1999, beach count increases of up to 7%yr-1

were observed. This is the highest estimate 

of the maximum net productivity rate (Rmax) 

observed for this species. Since 2000, low 

juvenile survival, thought to be due largely to food limitation, has been widespread with rare exception in the 

NWHI, resulting in the population decline (Fig. 1). While the MHI monk seal population may be on the rise (Baker 

and Johanos 2004), this remains unconfirmed and abundance appears to be too low to strongly influence current 

total stock trends. 

POTENTIAL BIOLOGICAL REMOVAL

 Potential biological removal (PBR) is designed to allow stocks to recover to, or remain above, the 

maximum net productivity level (MNPL) (Wade 1998). An underlying assumption in the application of the PBR 

equation is that marine mammal stocks exhibit certain dynamics. Specifically, it is assumed that a depleted stock 

will naturally grow toward OSP (Optimum Sustainable Population), and that some surplus growth could be removed 

while still allowing recovery. The Hawaiian monk seal population is far below historical levels and has declined 

3.8% yr-1 on average since 1998. Thus, for unknown reasons, the stock’s dynamics do not conform to the underlying 

model for calculating PBR such that PBR for the Hawaiian monk seal is undetermined. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

 Human-related mortality has caused two major declines of the Hawaiian monk seal (Ragen 1999). In the 

1800s, this species was decimated by sealers, crews of wrecked vessels, and guano and feather hunters (Dill and 

Bryan 1912; Wetmore 1925; Bailey 1952; Clapp and Woodward 1972). Following a period of at least partial 

recovery in the first half of the 20th century (Rice 1960), most subpopulations again declined. This second decline 

44
has not been fully explained, but trends at several sites appear to have been determined by human disturbance from 

military or U.S. Coast Guard activities (Ragen 1999; Kenyon 1972; Gerrodette and Gilmartin 1990). Currently, 

human activities in the NWHI are limited and human disturbance is relatively rare, but human-seal interactions have 

become an important issue in the MHI. 

Fishery Information

 Fishery interactions with monk seals can include direct interaction with gear (hooking or entanglement), 

seal consumption of discarded catch, and competition for prey. Entanglement of monk seals in derelict fishing gear, 

which is believed to originate outside the Hawaiian archipelago, is described in a separate section below. 

 In the past, monk seal interactions with fisheries in the NWHI were documented, but direct interactions 

have since become rare or non-existent, and issues related to competition have also somewhat abated. For example, 

in 1986 a seal died from entanglement in the bridle rope of lobster trap set in the NWHI lobster fishery. Possible 

reduction of monk seal prey by that fishery (through removal of both target and bycatch species) has also been 

raised as a concern, though whether the fishery indirectly impacted monk seals remains unresolved. However, the 

NWHI lobster fishery closed in 2000 and on June 15, 2006, President Bush signed a proclamation that created the 

Northwestern Hawaiian Islands Marine National Monument. Subsequent regulations prohibit commercial fishing in 

the Monument except for the bottomfish fishery (and associated pelagic species catch), which may continue for no 

more than 5 years (U.S. Department of Commerce and Department of the Interior, 2006). In the past, interactions 

between the Hawaii-based domestic pelagic longline fishery and monk seals were documented (NMFS 2002). This 

fishery targets swordfish and tunas and does not compete with Hawaiian monk seals for prey. In October 1991, in 

response to 13 unusual seal wounds thought to have resulted from interactions with this fishery, NMFS established a 

Protected Species Zone extending 50 nautical miles around the NWHI and the corridors between the islands. 

Subsequently, no additional monk seal interactions with the longline fishery have been confirmed. Since 1991, there 

have been no observed or reported interactions of this fishery with monk seals. 

 The NWHI bottomfish handline fishery has been reported to interact with monk seals. This fishery landed 

between 95 and 201 metric tons per year from 1989-2005 (Kawamoto 1995; Kawamoto, pers. comm.) and the 

number of vessels is currently capped at 9 (8 made NWHI trips in 2005, Kawamoto, pers. comm.). Nitta and 

Henderson (1993) documented reports of seals taking bottomfish and bait off fishing lines, and reports of seals 

attracted to discarded bycatch. A Federal observer program of the fishery began in the fourth quarter of 2003 and no 

monk seal interactions have been observed to date. NMFS prepared a Section 7 Biological Opinion on the Fishery 

Management Plan for the bottomfish fishery, and concluded that the operation of this fishery is not likely to 

jeopardize the continued existence of the Hawaiian monk seal nor would it likely destroy or adversely modify the 

monk seal’s critical habitat (NMFS 2002). The Biological Opinion has no incidental take statement. An EIS for the 

bottomfish fishery management plan has also been prepared. Fishermen indicate that they have engaged in 

mitigating activity over the past several years, e.g., holding discards on-board, etc. (NMFS pers. comm.). The 

ecological effects of this fishery on monk seals (e.g., competition for prey or alteration of prey assemblages) are 

unknown. However, published studies on monk seal prey selection based upon scat/spew analysis and seal-mounted 

video revealed some evidence that monk seals fed on families of bottomfish which contain commercial species 

(many prey items recovered from scats and spews were identified only to the level of family; Goodman-Lowe 1998, 

Longenecker et al. 2006, Parrish et al. 2000). Recent efforts have expanded bottomfish species representation in a 

fatty acid library to help clarify their potential importance in the monk seal diet using quantitative fatty acid 

signature analysis. Results of this research effort are expected to be available in 2007. As noted above, this fishery is 

slated to be closed by 2011. 

 In contrast to the NWHI, fishery interactions are a serious concern in the MHI, especially involving State of 

Hawaii managed nearshore fisheries. One seal was found dead in a nearshore (non-recreational) gillnet in 1994 and 

a second seal was found dead in 1995 with a hook lodged in its esophagus. A total of 32 seals have been observed 

with embedded hooks in the MHI during 1990-2005. Several incidents, including the dead hooked seal mentioned 

above, involved hooks used to catch ulua (jacks, Caranx spp.). Interactions in the MHI appear to be on the rise, as 

most hookings have occurred since 2000, and three seals have been observed entangled in nearshore gillnets since 

2002 (NMFS unpubl. data). The 2005 nearshore fishery serious injury, reported in Table 1, involved a seal observed 

entangled and struggling in a nearshore gillnet off Oahu. By the time a NMFS contract veterinarian arrived on the 

scene, the seal was gone and fishermen were retrieving the net, which had a large hole presumably where the seal 

had been caught. Because it was not possible to determine whether the seal escaped uninjured, entangled, or whether 

it had died, this case was judged as a serious injury. The MHI bottomfish handline fishery also has potential to 

interact with monk seals, though no mortalities or serious injuries have been attributed to the fishery (Table 1). 

45
Table 1. Summary of mortality and serious injury of Hawaiian monk seals due to fisheries and calculation of annual 

mortality rate. n/a indicates that sufficient data are not available. 

Fishery Name Year Data 

Type 

% Obs. 

coverage 

Observed/Reported 

Mortality/Serious Injury 

Estimated 

Mortality/ 

Serious Injury 

Mean 

Takes 

(CV) 

NWHI Lobster 2000-present fishery closed 

Pelagic 

Longline 

2001 

2002 

2003 

2004 

2005 

observer 

observer 

observer 

observer 

observer 

22.5% 

24.6% 

22.2% 

24.6% 

26.1% & 

100%1

 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0 (0) 

NWHI 

Bottomfish 

2001-2002 

20032

2004 

2005 

Logbook 

observer 

observer 

observer 

n/a 

33% 

18.3% 

25.0% 

n/a 

0 

0 

0 

n/a 

0 

0 

0 

0 (0) 

MHI 

Bottomfish3

2001 

2002 

2003 

2004 

2005 

n/a none 

0 

0 

0 

0 

0 

0 

n/a n/a 

Nearshore3 2001 

2002 

2003 

2004 

2005 

n/a none 

0 

1 

1 

1 

2 

1 

n/a n/a 

 

Fishery Mortality Rate

 Total fishery mortality and serious injury cannot be considered to be insignificant and approaching a rate of 

zero. Monk seals are being hooked and entangled in the MHI at a rate which has not been reliably assessed. The 

information above represents only reported direct interactions and without purpose-designed observation effort the 

true interaction rate cannot be estimated. Monk seals also die from entanglement in fishing gear and other debris 

throughout their range (likely originating from various countries), and NMFS along with partner agencies, is 

pursuing a program to mitigate entanglement (see below). Indirect interactions (i.e., involving competition for prey 

or consumption of discards) remain the topic of ongoing investigation. 

Entanglement in Marine Debris

 Hawaiian monk seals become entangled in fishing and other marine debris at rates higher than reported for 

other pinnipeds (Henderson 2001). A total of 261 cases of seals entangled in fishing gear or other debris have been 

observed through 2005 (Henderson 2001; NMFS, unpubl. data), including seven documented mortalities resulting 

from entanglement in fisheries debris (Henderson 1990, 2001; NMFS, unpubl. data). The fishing gear fouling the 

reefs and beaches of the NWHI and entangling monk seals only rarely includes types used in Hawaiian fisheries. 

For example, trawl net and monofilament gillnet accounted for approximately 35% and 34% of the debris removed 

from reefs in the NWHI by weight, and trawl net alone accounted for 88% of the debris by frequency (Donohue et 

al. 2001). Yet there are no commercial trawl fisheries in Hawaii. 

 The NMFS and partner agencies continue to mitigate impacts of marine debris on monk seals as well as 

turtles, coral reefs and other wildlife. Marine debris is removed from beaches and entangled seals during annual 

population assessment activities at the main reproductive sites. Since 1996, annual debris survey and removal efforts 

in the NWHI coral reef habitat have been ongoing (Donohue et al. 2000, Donohue et al. 2001). 

Other Mortality

 Since 1982, 23 seals died during rehabilitation efforts; additionally, two died in captivity, two died when 

captured for translocation, one was euthanized (an aggressive male known to cause mortality), three died during 

 

1 Observer coverage for deep and shallow-set components of the fishery, respectively. 2 Observer coverage began in fourth quarter of 2003. Data for that quarter provided. 3

Data for MHI bottomfish and nearshore fisheries are based upon incidental observations (i.e., hooked seals). All hookings not clearly attributable 

to either fishery with certainty were attributed to the bottomfish fishery, and hookings which resulted in injury of unknown severity were 

classified as serious.

46
captive research and three died during field research (Baker and Johanos 2002). In 2005, a weaned pup died while 

in NMFS care at a captive facility on Oahu for testing and potential treatment for leptospirosis. Post-mortem 

examination did not reveal a cause of death. 

 In 1986, a weaned pup died at East Island, French Frigate Shoals, after becoming entangled in wire left 

when the U.S. Coast Guard abandoned the island three decades earlier. In 1991, a seal died after becoming trapped 

behind an eroding seawall on Tern Island, French Frigate Shoals. The only documented case of illegal killing of a 

Hawaiian monk seal occurred when a resident of Kauai killed an adult female in 1989. 

 Other sources of mortality that impede recovery include food limitation (see Habitat Issues below), single 

and multiple-male aggression (mobbing), shark predation, and disease/parasitism. Multiple-male aggression has 

primarily been identified as a problem at Laysan and Lisianski Islands, though it has also been documented at other 

subpopulations. In 1994, 22 adult males were removed from Laysan Island, and only five seals are thought to have 

died from multiple-male aggression at this site since their removal (1995-2005). 

 Attacks by single adult males have resulted in several monk seal mortalities, most notably at French Frigate 

Shoals in 1997, where at least 8 pups died from this cause. Many more pups were likely killed in the same way but 

the cause of their deaths could not be confirmed. Two males that killed pups in 1997 were translocated to Johnston 

Atoll, 870 km to the southwest. Subsequently, mounting injury to pups has decreased. 

 Shark-related injury and mortality incidents appeared to have increased in the late 1980s and early 1990s at 

French Frigate Shoals, but such mortality was probably not the primary cause of the decline at this site (Ragen 

1993). However, shark predation has accounted for a significant portion of pup mortality in recent years. At French 

Frigate Shoals in 1999, 17 pups were observed injured by large sharks, and at least 3 were confirmed to have died 

from shark predation (Johanos and Baker 2001). As many as 22 pups of a total 92 born at French Frigate Shoals in 

1999 were likely killed by sharks. After 1999, losses of pups to shark predation have been fewer, but this source of 

mortality remains a serious concern. Various mitigation efforts have been undertaken by NMFS in cooperation with 

the U. S. Fish and Wildlife Service (USFWS), which manages French Frigate Shoals as part of the Hawaiian Islands 

National Wildlife Refuge. 

 An Unusual Mortality Event (UME) contingency plan has recently been published for the monk seal 

(Yochem et al. 2004). While disease effects on monk seal demographic trends are uncertain, there is concern that 

diseases of livestock, feral animals, pets or humans could be transferred to naive monk seals in the main Hawaiian 

Islands and potentially spread to the core population in the NWHI. Recent diagnoses (R. Braun, pers. comm.) 

confirm that in 2003 and 2004, two deaths of free-ranging monk seals are attributable to diseases not previously 

found in the species: leptospirosis and toxoplasmosis. Leptospira bacteria are found in many of Hawaii's streams 

and estuaries and are associated with livestock and rodents. Cats, domestic and feral, are a common source of 

toxoplasma. 

STATUS OF STOCK

 In 1976, the Hawaiian monk seal was designated depleted under the Marine Mammal Protection Act of 

1972 and as endangered under the Endangered Species Act of 1973. The species is well below its OSP and has not 

recovered from past declines. Therefore, the Hawaiian monk seal is characterized as a strategic stock. 

Habitat Issues

 Vessel groundings pose a continuing threat to monk seals and their habitat, through potential physical 

damage to reefs, oil spills, and release of debris into habitats. The substantial decline at French Frigate Shoals is 

likely related to lack of available prey and subsequent emaciation and starvation. Two leading hypotheses to explain 

the lack of prey are 1) the local population reached its carrying capacity in the 1970s and 1980s, diminishing its own 

food supply, and 2) carrying capacity was simultaneously reduced by changes in oceanographic conditions and a 

subsequent decline in productivity (Polovina et al. 1994; Craig and Ragen 1999). Similarly, recently observed poor 

juvenile survival rates suggest that prey availability may be limiting recovery of other NWHI subpopulations. 

 Goodman-Lowe (1998) provided information on prey selection using hard parts in scats and spewings. 

Information on at-sea movement and diving is available for seals at all six main subpopulations in the NWHI using 

satellite telemetry (Stewart et al. 2006). Preliminary studies to describe the foraging habitat of monk seals in the 

MHI are reported in Littnan et al. (2006). 

 Tern Island is the site of a USFWS refuge station, and is one of two sites in the NWHI accessible by 

aircraft. During World War II, the U.S. Navy enlarged the island to accommodate the runway, and a sheet-pile 

seawall was constructed to maintain the modified shape of the island. Degradation of the seawall created entrapment 

hazards for seals and other wildlife. Erosion of the sea wall also raised concerns about the potential release of toxic 

wastes into the ocean. The USFWS began construction on the Tern Island sea wall in 2004 to reduce entrapment 

47
hazards and protect the island shoreline. The USFWS considers this a high priority project to complete, and is 

pursuing funding to that end. 

 Another habitat issue involves loss of terrestrial habitat at French Frigate Shoals, where pupping and 

resting islets have shrunk or virtually disappeared (Antonelis et al. 2006). Projected increases in global average sea 

level (Church et al. 2001) may further significantly reduce terrestrial habitat for monk seals in the NWHI (Baker, 

Littnan and Johnston, 2006). 

 There are indications that monk seal abundance is increasing in the main Hawaiian Islands (Baker and 

Johanos 2004). Further, the excellent condition of pups weaned on these islands suggests that there may be ample 

prey resources available. If the monk seal population does expand in the MHI, it may bode well for the species’ 

recovery and long-term persistence. In contrast, there are many challenges that may limit the potential for growth in 

this region. The human population in the MHI is approximately 1.2 million compared to fewer than 100 in the 

NWHI, so that the potential impact of disturbance in the MHI is great. As noted above, the hooking of monk seals 

by fishermen in the MHI is another source of injury and mortality. Finally, vessel traffic in the populated islands 

carries the potential for collision with seals and impacts from oil spills. Thus, issues surrounding monk seals in the 

main Hawaiian Islands will likely become an increasing focus for management and recovery of this species. 

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96822-2396. 34 pp. 

Ragen, T. J. 1993. Status of the Hawaiian monk seal in 1992. Admin. Rep. H-93-05. Southwest Fisheries Science 

Center, National Marine Fisheries Service, 2570 Dole St., Honolulu, HI 96822-2396. 79 pp. 

Ragen, T.J. 1999. Human activities affecting the population trends of the Hawaiian monk seal. Pages 183-194 in

J.A. Musick, ed. Life in the slow lane: Ecology and conservation of long-lived marine animals. American 

Fisheries Society Symposium 23, American Fisheries Society, Bethesda, MD. 

Rexstad, E. A., and K. P. Burnham. 1991. User's manual for interactive Program CAPTURE. Colorado 

Cooperative Fish and Wildlife Research Unit, Colorado State University, Fort Collins, CO. 29 pp. 

49
Rice, D. W. 1960. Population dynamics of the Hawaiian monk seal. J. Mammal. 41:376-385. 

Stewart B. S., G. A. Antonelis, J. D. Baker, and P.Y.Yochem. 2006. Foraging biogeography of the Hawaiian monk 

seal in the Northwestern Hawaiian Islands. Atoll Res Bull 543:131-145. 

U.S. Department of Commerce and Department of the Interior. 2006. Northwestern Hawaiian Islands Marine 

National Monument. Federal Register 71:51,134-51,142. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

Wade, P. R. 1998. Calculating limits to the allowable human-caused mortality of cetaceans and pinnipeds. Marine 

Mammal Science 14:1-37. 

Wetmore, A. 1925. Bird life among lava rock and coral sand. The Natl. Geograp. Mag. 48:77-108. 

White, G. C., D. R. Anderson, K. P. Burnham, and L. Otis. 1982. Capture-recapture and removal methods for 

sampling closed populations. Los Alamos National Laboratory, Los Alamos, New Mexico. 

Yochem, P. K., R. C. Braun, B. Ryon, J. D. Baker, and G. A. Antonelis. 2004. Contingency plan for Hawaiian monk 

seal Unusual Mortality Events. NOAA-TM-NMFS-PIFSC-2, 27 p. 

50
Revised 03/15/2005 

HARBOR PORPOISE (Phocoena phocoena): Morro Bay Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

In the Pacific, harbor porpoise are found 

in coastal and inland waters from Point 

Conception, California to Alaska and across to

Kamchatka and Japan (Gaskin 1984). Harbor 

porpoise appear to have more restricted 

movements along the western coast of the

continental U.S. than along the eastern coast. 

Regional differences in pollutant residues in 

harbor porpoise indicate that they do not move 

extensively between California, Oregon, and 

Washington (Calambokidis and Barlow 1991). 

That study also showed some regional differences

within California (although the sample size was 

small). This pattern stands as a sharp contrast to 

the eastern coast of the U.S. and Canada where 

harbor porpoise are believed to migrate seasonally

from as far south as the Carolinas to the Gulf of 

Maine and Bay of Fundy (Polacheck et al. 1995).

A phylogeographic analysis of genetic data from

northeast Pacific harbor porpoise did not show

complete concordance between DNA sequence

types and geographic location (Rosel 1992).

However, an analysis of molecular variance

(AMOVA) of the same data with additional 

samples found significant genetic differences for 

four of the six pair-wise comparisons between the 

four areas investigated: California, Washington, 

British Columbia, and Alaska (Rosel et al. 1995). 

These results demonstrate that harbor porpoise

along the west coast of North America are not

panmictic or migratory, and movement is

sufficiently restricted that genetic differences 

have evolved. Recent preliminary genetic 

analyses of samples ranging from Monterey Bay, California to Vancouver Island, British Columbia indicate

that there is small-scale subdivision within the U.S. portion of this range (Chivers et al., 2002). 

W128.0 W126.0 W124.0 W122.0 W120.0 W118.0

N34.0

N36.0

N38.0

N40.

N42.

N44.

0

0

0

Oregon

California Northern California/

Southern Oregon

San FranciscoRussian River

Monterey

 Bay

Morro Bay

Cape Blanco

Monterey Bay

Cape Mendocino

Point Conception

Point Arena

Morro Bay

Oregon/Washington

 coast

Russian River

Figure 1. Stock boundaries and distributional range

of harbor porpoise along the California/southern

Oregon coast. Shaded area represents harbor 

porpoise habitat (0-200 m) along the U.S. west

coast. 

In their assessment of harbor porpoise, Barlow and Hanan (1995) recommended that the animals 

inhabiting central California (defined to be from Point Conception to the Russian River) be treated as a

separate stock. Their justifications for this were: 1) fishery mortality of harbor porpoise is limited to

central California, 2) movement of individual animals appears to be restricted within California, and 

consequently 3) fishery mortality could cause the local depletion of harbor porpoise if central California is

not managed separately. Although geographic structure exists along an almost continuous distribution of 

harbor porpoise from California to Alaska, stock boundaries are difficult to draw because any rigid line is

(to a greater or lesser extent) arbitrary from a biological perspective. Nonetheless, failure to recognize 

geographic structure by defining management stocks can lead to depletion of local populations. Based on

recent genetic findings (Chivers et al., 2002), California coast stocks were re-evaluated, and significant

genetic differences were found among 4 identified sampling sites. Revised stock boundaries are presented

here based on these genetic data and density discontinuities identified from aerial surveys, resulting in six

California/Oregon/Washington stocks where previously there had been four (Carretta et al. 2001a). The 

stock boundaries for animals that occur in California/southern Oregon waters are shown in Figure 1. For

the 2004 Marine Mammal Protection Act (MMPA) Stock Assessment Reports, other Pacific coast harbor

porpoise stocks include: 1) a Monterey Bay stock, 2) a San Francisco-Russian River stock, 3) a northern

California/southern Oregon stock, 4) an Oregon/Washington coast stock, 5) an Inland Washington stock,

51
6) a Southeast Alaska stock, 7) a Gulf of Alaska stock, and 8) a Bering Sea stock. Stock assessment reports

for Monterey Bay, San Francisco-Russian River, northern California/southern Oregon, Oregon/Washington

coast, and Inland Washington waters harbor porpoise appear in this volume. The three Alaska harbor

porpoise stocks are reported separately in the Stock Assessment Reports for the Alaska Region. 

POPULATION SIZE

Previous estimates of abundance for California harbor porpoise were based on aerial surveys 

conducted between the coast and the 50-fm isobath during 1988-95 (Barlow and Forney 1994, Forney

1999a). These estimates did not include an unknown number of animals found in deeper waters. Barlow

(1988) found that the vast majority of harbor porpoise in California were within the 0-50-fm depth range;

however, Green et al. (1992) found that 24% of harbor porpoise seen during aerial surveys of Oregon and 

Washington were between the 100m and 200m isobaths (55 to 109 fathoms). A systematic ship survey of

depth strata out to 90 m in northern California showed that porpoise abundance declined significantly in

waters deeper than 60 m (Carretta et al. 2001b). A recent analysis of harbor porpoise trends including 

oceanographic data suggests that the proportion of California harbor porpoise in deeper waters may vary

between years (Forney 1999b). In 1999 and 2002, aerial surveys extended farther offshore (to the 200m 

depth contour or a minimum of 10 nmi from shore in the region of the Morro Bay stock) to provide a more 

complete abundance estimate. Based on 1999 and 2002 aerial surveys under good survey conditions

(Beaufort ≤2, cloud cover ≤25%) the estimate of abundance for this stock is 1,656 animals (CV = 0.39) 

(Carretta and Forney 2004 ).

 

Minimum Population Estimate

The minimum population estimate for the Morro Bay harbor porpoise stock is taken as the lower

20th percentile of the log-normal distribution of the abundance estimated from the 1999-2002 aerial

surveys, or 1,206 animals. 

Current Population Trend

Analyses of a 1986-95

time series of aerial surveys have

been conducted to examine

trends in harbor porpoise

abundance in central California 

(Forney, 1995; 1999b). After 

controlling for the effects of sea 

state, cloud cover, and area on

sighting rates, Forney (1995) 

found a negative trend in

population size; however, that

trend was no longer significant 

when sea surface temperature (a 

proxy measure of oceanographic

conditions) was included in an 

updated non-linear trend analysis

(Forney 1999b). The negative 

correlation between harbor

porpoise sighting rates and sea

surface temperatures indicates that apparent trends could be caused by changing oceanographic conditions 

and movement of animals into and out of the study area. Encounter rates for the 1997 survey, however,

were very high (Forney 1999a) despite the warmer sea surface temperatures caused by strong El Niño 

conditions. These observations suggest that patterns of harbor porpoise movement are not directly related

to sea surface temperature, but rather to the more complex distribution of potential prey species in this area. 

There has been an increasing trend in porpoise abundance in the Morro Bay stock since 1988, which is

statistically significant (p < 0.002), Figure 2. More detailed studies of encounter rate patterns in relation to

satellite-derived sea surface temperature are planned to shed light on potential oceanography-related

movement patterns of harbor porpoise in this region. 

Morro Bay

0

1000

2000

3000

4000

5000

198819891990199119921993199419951996199719981999200020012002

Year

Porpoise Abundance

Figure 2. Aerial survey estimates of abundance for the Morro Bay 

stock of harbor porpoise, 1988-2002. Error bars represent lower 

and upper 95% confidence intervals. Solid line represents a linear 

regression on the natural logarithm of abundance over time. The 

slope of this regression is statistically significant (p < 0.002). 

52
CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 Based on what are argued to be biological limits of the species (i.e. females give birth first at age 4 

and produce one calf per year until death), the theoretical, maximum-conceivable growth rate of a closed 

harbor porpoise population was estimated as 9.4% per year (Barlow and Boveng 1991). This maximum 

theoretical rate may not be achievable for any real population. [Woodley and Read (1991) calculate a 

maximum growth rate of approximately 5% per year, but their argument for this being a maximum (i.e. that 

porpoise survival rates cannot exceed those of Himalayan thar) is not well justified.] Population growth 

rates have not actually been measured for any harbor porpoise population. Because a reliable estimate of 

the maximum net productivity rate is not available for Morro Bay harbor porpoise, we use the default 

maximum net productivity rate (RMAX) of 4% for cetaceans (Wade and Angliss 1997) be employed. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum 

population size (1,206) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times

a recovery factor of 0.4 (for a stock of unknown status with a mortality rate CV ≥ 0.80; Wade and Angliss 

1997), resulting in a PBR of 10. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

 The set gillnet fishery for halibut and angel shark has operated in the vicinity of Morro Bay, and 

fishing effort there peaked in 2001. A ban on set gillnets inshore of 60 fathoms from Point Arguello to 

Point Reyes, California, has been in place since September 2002. California Department of Fish and Game 

(CDFG) estimated fishing effort for 1998-2002 in this fishery is 139, 121, 284, 391, and 21 days 

respectively. Mortality rates of harbor porpoise in the set gillnet fishery in this region are available only 

from 43 trips observed between 1990-94 (Julian and Beeson 1998), in which one harbor porpoise was 

killed. This represents a kill rate of 0.023 porpoise/day fished (bootstrap CV = 0.97). Projected mortality 

levels based on this kill rate and effort levels for 1998-2002 are summarized in Table 1. It should be noted 

that this kill rate includes sets made in less than 30 fathoms of water, where the potential to entangle 

porpoise is higher. The white seabass set gillnet fishery also has operated in the vicinity of Morro Bay, 

and this fishery has been documented to take harbor porpoise in the past (Norris and Prescott 1961). Effort 

in the white seabass fishery in the vicinity of Morro Bay for the last five years (1998-2002) has been 26, 7, 

61, 132, and 32 fishing days respectively. Because of the aforementioned depth restrictions for gillnets in 

this region, it is expected that harbor porpoise interactions with the white seabass set gillnet fishery would 

be near zero. 

Table 1. Summary of available information on incidental mortality and injury of harbor porpoise (Morro 

Bay stock) in commercial fisheries that might take this species (Cameron and Forney 2000, Carretta 2001, 

Forney et al., 2001; Carretta 2002, Carretta and Chivers 2003). Mean annual takes are based on 1998-

2002 data unless noted otherwise. 

Fishery Name Year(s) Data Type 

Percent 

Observer 

Coverage

Observed 

Mortality Kill/Day 

Estimated 

Mortality 

(CV in 

parentheses) 

Mean Annual Takes

(CV in parentheses)

CA angel shark / halibut 

and other species large 

mesh (>3.5") set gillnet 

fishery

1998 

1999 

2000 

2001 

2002 

1990-94 

observer data

Fishery closed 

permanently 

in waters < 60 

fathoms 

0% 

0% 

0% 

0% 

- 

- 

- 

- 

- 

0.0231

3 (0.97) 

3 (0.97) 

7 (0.97) 

9 (0.97) 

0.5 (n/a) 

 4.5 (0.97)2

Minimum total annual takes 4.5 (0.97)2

1

Mortality rate is based on 1 observed mortality from 43 observed trips in this region between 1990-94. 2

Mean annual takes are based on 1998-2002 effort data and 1990-94 kill rates.

53
Both of the above central California gillnet fisheries were restricted by a series of emergency 

closures beginning in September 2000, because of concern over mortality of Common Murres and a decline 

in the southern sea otter population. During the emergency closure, fishing was allowed in waters deeper 

than 30 fathoms between Yankee Point (Monterey County) and Pt. Sal (Santa Barbara County) until April 

2002, and fishing effort initially increased within the range of the Morro Bay harbor porpoise stock. A ban 

on the use of gill and trammel nets in all ocean waters 60 fathoms or less between Point Reyes (Marin 

County) and Point Arguello (Santa Barbara County) became effective on September 4, 2002. The ban is 

expected to virtually eliminate bycatch of Morro Bay harbor porpoise in these two gillnet fisheries, because 

this species is primarily found in waters shallower than 60 fathoms. 

STATUS OF STOCK

Harbor porpoise in California are not listed as threatened or endangered under the Endangered 

Species Act nor as depleted under the Marine Mammal Protection Act. Barlow and Hanan (1995) calculate 

the status of harbor porpoise relative to historic carrying capacity (K) using a technique called backprojection. They calculate that the central California population (including Morro Bay, Monterey Bay, and 

San Francisco-Russian River stocks) could have been reduced to between 30% and 97% of K by incidental 

fishing mortality, depending on the choice of input parameters. They conclude that there is no practical 

way to reduce the range of this estimate. New information does not change this conclusion, and the status 

of central California harbor porpoise populations relative to their Optimum Sustainable Population (OSP) 

levels must be treated as unknown. 

 Based on the last 5 years of fishing effort (1998-2002), mean annual takes are 4.5 porpoise per 

year, which is less than the PBR of 10 animals, resulting in a “non-strategic” classification. A set gillnet 

closure inside of 60 fathoms was finalized in September 2002, effectively eliminating set gillnets from 

most harbor porpoise habitat in the region of this stock. This is expected to reduce fishery mortality of 

Morro Bay harbor porpoise to near zero. Although in recent years the average fishery mortality exceeded 

10% of the PBR and, therefore, cannot be considered to be insignificant and approaching zero mortality 

and injury rate, it is likely that this goal will be met following the 2002 gillnet closure. Research activities 

will continue to monitor the population size and to investigate population trends. There are no known 

habitat issues that are of particular concern for this stock. 

REFERENCES

Barlow, J. 1988. Harbor porpoise (Phocoena phocoena) abundance estimation in California, Oregon and 

Washington: I. Ship surveys. Fish. Bull. 86:417-432. 

Barlow, J. and P. Boveng. 1991. Modeling age-specific mortality for marine mammal populations. Mar. 

Mamm. Sci. 7(1):84-119. 

Barlow, J. and K. A. Forney. 1994. An assessment of the 1994 status of harbor porpoise in California. 

U.S. Dep. Commer., NOAA Tech. Memo. NMFS-SWFSC-205. 17 pp. 

Barlow, J. and D. Hanan. 1995. An assessment of the status of harbor porpoise in central California. 

Rept. Int. Whal., Special Issue 16:123-140. 

Calambokidis, J. and J. Barlow. 1991. Chlorinated hydrocarbon concentrations and their use for 

describing population discreteness in harbor porpoises from Washington, Oregon, and California. 

pp. 101-110 In: J. E. Reynolds III and D. K. Odell (eds.) Marine mammal strandings in the United 

States. NOAA Tech. Rep. NMFS 98. 

Carretta, J.V. 2001. Preliminary estimates of cetacean mortality in California gillnet fisheries for 2000. 

Paper SC/53/SM9 presented to the International Whaling Commission (unpublished). 21pp. 

Carretta, J.V., J. Barlow, K.A. Forney, M.M. Muto, and J. Baker. 2001a. U.S. Pacific Marine Mammal 

Stock Assessments: 2001. U.S. Dep. Commer. NOAA Technical Memorandum NMFS-SWFSC317. 280pp. 

Carretta, J.V., B.L. Taylor, and S.J. Chivers. 2001b. Abundance and depth distribution of harbor porpoise 

(Phocoena phocoena) in northern California determined from a 1995 ship survey. U.S. Fishery 

Bulletin 99:29-39. 

Carretta, J.V. 2002. Preliminary estimates of cetacean mortality in California gillnet fisheries for 2001. 

Paper SC/54/SM12 presented to the International Whaling Commission (unpublished). 22pp. 

Carretta, J.V. 2003. Preliminary estimates of harbor porpoise abundance in California from 1997 and 1999 

aerial surveys. Southwest Fisheries Science Center Administrative Report LJ-03-04. 12 p. 

54
Carretta, J.V. and S.J. Chivers. 2003. Preliminary estimates of marine mammal mortality and biological 

sampling of cetaceans in California gillnet fisheries for 2002. Paper SC/55/SM3 presented to the 

International Whaling Commission (unpublished). 21pp. 

Carretta, J.V. and K.A. Forney. 2004. Preliminary estimates of harbor porpoise abundance in California 

from 1999 and 2002 aerial surveys. SWFSC Administrative Report LJ-04-01, available from 

Southwest Fisheries Science Center, 8604 La Jolla Shores Drive, La Jolla, CA, USA. 13pp. 

Chivers, S.J., A.E. Dizon, P.J. Gearin, and K.M. Robertson. 2002. Small-scale population structure of 

eastern North Pacific harbour porpoises, (Phocoena phocoena), indicated by molecular genetic 

analyses. Journal of Cetacean Research and Management 4(2):111-122. 

Forney, K.A., D.A. Hanan, and J. Barlow. 1991. Detecting trends in harbor porpoise abundance from 

aerial surveys using analysis of covariance. U.S. Fishery Bulletin 89:367-377. 

Forney, K. A. 1999a. The abundance of California harbor porpoise estimated from 1993-97 aerial linetransect surveys. Admin. Rep. LJ-99-02. Southwest Fisheries Center, National Marine Fisheries 

Service, P.O. Box 271, La Jolla, CA 92038. 16 pp. 

Forney, K. A. 1999b. Trends in harbor porpoise abundance off central California, 1986-95: Evidence for 

interannual changes in distribution? J. Cetacean Res. Manage. 1:73-80. 

Gaskin, D. E. 1984. The harbour porpoise (Phocoena phocoena L.): regional populations, status, and 

information on direct and indirect catches. Rep. int. Whal. Commn 34:569_586. 

Green, G. A., J. J. Brueggeman, R. A. Grotefendt, C. E. Bowlby, M. L. Bonnell, and K. C. Balcomb, III. 

1992. Cetacean distribution and abundance off Oregon and Washington, 1989-1990. Ch. 1 In: J. 

J. Brueggeman (ed.). Oregon and Washington Marine Mammal and Seabird Surveys. Minerals 

Management Service Contract Report 14-12-0001-30426 prepared for the Pacific OCS Region. 

Julian, F. and M. Beeson. 1998. Estimates of mammal, turtle, and bird mortality for two California gillnet 

fisheries: 1990-1995. U.S. Fishery Bulletin 96:271-284. 

Laake, J. L., J. C. Calambokidis, S. D. Osmek, and D. J. Rugh. 1997. Probability of detecting harbor 

porpoise from aerial surveys: estimating g(0). J. Wildl. Manag. 61:63-75. 

NMFS, Southwest Fisheries Science Center, P.O. Box 271, La Jolla, CA 92038-0271. 

NMFS, Southwest Region, 501 West Ocean Blvd, Long Beach, CA 90802_4213. 

Norris, K.S. and J.H. Prescott. 1961. Observations on Pacific cetaceans of Californian and Mexican 

waters. Univ. Calif. Publ. Zool. 63(4):291-402. 

Polacheck, T., F. W. Wenzel, and G. Early. 1995. What do stranding data say about harbor porpoise 

(Phocoena phocoena). Rep. Int. Whal. Comm., Special Issue 16:169-179. 

Rosel, P. E. 1992. Genetic population structure and systematic relationships of some small cetaceans 

inferred from mitochondrial DNA sequence variation. Ph.D. Dissertation, Univ. Calif. San Diego. 

191pp. 

Rosel, P. E., A. E. Dizon, and M. G. Haygood. 1995. Variability of the mitochondrial control region in 

populations of the harbour porpoise, Phocoena phocoena, on inter-oceanic and regional scales. 

Can. J. Fish. and Aquat. Sci. 52:1210-1219. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the 

GAMMS Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. 

Memo. NMFS-OPR-12. 93 pp. 

Woodley, T. H. and A. J. Read. 1991. Potential rates of increase of a harbour porpoise (Phocoena 

phocoena) population subjected to incidental mortality in commercial fisheries. Can. J. Fish. 

Aquat. Sci. 48:2429-2435.

55
Revised 03/15/2005 

HARBOR PORPOISE (Phocoena phocoena): Monterey Bay Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

In the Pacific, harbor porpoise are found 

in coastal and inland waters from Point 

Conception, California to Alaska and across to

Kamchatka and Japan (Gaskin 1984). Harbor 

porpoise appear to have more restricted 

movements along the western coast of the

continental U.S. than along the eastern coast. 

Regional differences in pollutant residues in 

harbor porpoise indicate that they do not move 

extensively between California, Oregon, and 

Washington (Calambokidis and Barlow 1991). 

That study also showed some regional differences

within California (although the sample size was 

small). This pattern stands as a sharp contrast to 

the eastern coast of the U.S. and Canada where 

harbor porpoise are believed to migrate seasonally

from as far south as the Carolinas to the Gulf of 

Maine and Bay of Fundy (Polacheck et al. 1995).

A phylogeographic analysis of genetic data from

northeast Pacific harbor porpoise did not show

complete concordance between DNA sequence

types and geographic location (Rosel 1992).

However, an analysis of molecular variance

(AMOVA) of the same data with additional 

samples found significant genetic differences for 

four of the six pair-wise comparisons between the 

four areas investigated: California, Washington,

British Columbia, and Alaska (Rosel et al. 1995). 

These results demonstrate that harbor porpoise

along the west coast of North America are not

panmictic or migratory, and movement is

sufficiently restricted that genetic differences have

evolved. Recent preliminary genetic analyses of 

samples ranging from Monterey Bay, California to Vancouver Island, British Columbia indicate that there

is small-scale subdivision within the U.S. portion of this range (Chivers et al., 2002). 

W128.0 W126.0 W124.0 W122.0 W120.0 W118.0

N34.0

N36.0

N38.0

N40.

N42.

N44.

0

0

0

Oregon

California Northern California/

Southern Oregon

San FranciscoRussian River

Monterey

 Bay

Morro Bay

Cape Blanco

Monterey Bay

Cape Mendocino

Point Conception

Point Arena

Morro Bay

Oregon/Washington

 coast

Russian River

Figure 1. Stock boundaries and distributional

range of harbor porpoise along the 

California/southern Oregon coast. Shaded are

represents harbor porpoise habitat (0-200 m)

along the U.S. west coast.

In their assessment of harbor porpoise, Barlow and Hanan (1995) recommended that the animals 

inhabiting central California (defined to be from Point Conception to the Russian River) be treated as a

separate stock. Their justifications for this were: 1) fishery mortality of harbor porpoise is limited to

central California, 2) movement of individual animals appears to be restricted within California, and 

consequently 3) fishery mortality could cause the local depletion of harbor porpoise if central California is

not managed separately. Although geographic structure exists along an almost continuous distribution of 

harbor porpoise from California to Alaska, stock boundaries are difficult to draw because any rigid line is

(to a greater or lesser extent) arbitrary from a biological perspective. Nonetheless, failure to recognize 

geographic structure by defining management stocks can lead to depletion of local populations. Based on

recent genetic findings (Chivers, et al. 2002), California coast stocks were re-evaluated, and significant

genetic differences were found among 4 identified sampling sites. Revised stock boundaries are presented

here based on these genetic data and density discontinuities identified from aerial surveys, resulting in six

California/Oregon/Washington stocks where previously there had been four (Carretta et al. 2001a). The 

stock boundaries for animals that occur in California/southern Oregon waters are shown in Figure 1. For

the 2003 Marine Mammal Protection Act (MMPA) Stock Assessment Reports, other Pacific coast harbor

porpoise stocks include: 1) a Morro Bay stock, 2) a San Francisco-Russian River stock, 3) a northern

California/southern Oregon stock, 4) an Oregon/Washington coast stock, 5) a Washington Inland waters

56
stock, 6) a Southeast Alaska stock, 7) a Gulf of Alaska stock, and 8) a Bering Sea stock. Stock assessment

reports for Morro Bay, San Francisco-Russian River, northern California/southern Oregon,

Oregon/Washington coast, and Inland Washington waters harbor porpoise appear in this volume. The three

Alaska harbor porpoise stocks are reported separately in the Stock Assessment Reports for the Alaska 

Region. 

POPULATION SIZE

Previous estimates of abundance for California harbor porpoise were based on aerial surveys 

conducted between the coast and the 50-fm isobath during 1988-95 (Barlow and Forney 1994, Forney

1999a). These estimates did not include an unknown number of animals found in deeper waters. Barlow

(1988) found that the vast majority of harbor porpoise in California were within the 0-50-fm depth range;

however, Green et al. (1992) found that 24% of harbor porpoise seen during aerial surveys of Oregon and 

Washington were between the 100m and 200m isobaths (55 to 109 fathoms). A systematic ship survey of

depth strata out to 90 m in northern California showed that porpoise abundance declined significantly in

waters deeper than 60 m (Carretta et al. 2001b). A recent analysis of harbor porpoise trends including 

oceanographic data suggests that the proportion of California harbor porpoise in deeper waters may vary

between years (Forney 1999b). In 1999 and 2002, aerial surveys extended farther offshore (to the 200m 

depth contour or a minimum of 15 nmi from shore in the region of the Monterey Bay stock) to provide a

more complete abundance estimate. Based on 1999 and 2002 aerial surveys under good survey conditions

(Beaufort ≤2, cloud cover ≤25%) the estimate of abundance for this stock is 1,613 animals (CV = 0.42) 

(Carretta and Forney 2004).

 

Minimum Population Estimate

The minimum population estimate for the Monterey Bay harbor porpoise stock is taken as the

lower 20th percentile of the log-normal distribution of the abundance estimated from the 1999-2002 aerial

surveys, or 1,149 animals. 

Current Population Trend

Analyses of a 1986-95 time series of aerial surveys have been conducted to examine trends in 

harbor porpoise abundance in central California (Forney, 1995; 1999b). After controlling for the effects of

sea state, cloud cover, and area on sighting rates, Forney (1995) found a negative trend in population size;

however, that trend was no

longer significant when sea 

surface temperature (a proxy

measure of oceanographic

conditions) was included in an 

updated non-linear trend analysis

(Forney 1999b). The negative 

correlation between harbor

porpoise sighting rates and sea

surface temperatures indicates 

that apparent trends could be 

caused by changing 

oceanographic conditions and

movement of animals into and

out of the study area. Encounter 

rates for the 1997 survey, 

however, were very high (Forney

1999a) despite the warmer sea

surface temperatures caused by 

strong El Niño conditions. These 

observations suggest that patterns

of harbor porpoise movement are not directly related to sea surface temperature, but rather to the more 

complex distribution of potential prey species in this area. A linear regression of of the natural logarithm

of abundance over time for the Monterey Bay stock is not statistically significant (p=0.64, Figure 2). More 

detailed studies of encounter rate patterns in relation to satellite-derived sea surface temperature during 

Monterey Bay

0

1000

2000

3000

4000

5000

6000

198819891990199119921993199419951996199719981999200020012002

Year

Porpoise Abundance

Figure 2. Aerial survey estimates of abundance for the Monterey 

Bay stock of harbor porpoise, 1988-2002. Error bars represent

lower and upper 95% confidence intervals. Solid line represents a 

linear regression of the natural logarithm of abundance over time. 

The slope of this regression is not statistically significant (p = 0.64).

57
1993-99 are planned to shed light on potential oceanography-related movement patterns of harbor porpoise 

in this region. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES 

 Based on what are argued to be biological limits of the species (i.e. females give birth first at age 4 

and produce one calf per year until death), the theoretical, maximum-conceivable growth rate of a closed 

harbor porpoise population was estimated as 9.4% per year (Barlow and Boveng 1991). This maximum 

theoretical rate may not be achievable for any real population. [Woodley and Read (1991) calculate a 

maximum growth rate of approximately 5% per year, but their argument for this being a maximum (i.e. that 

porpoise survival rates cannot exceed those of Himalayan thar) is not well justified.] Population growth 

rates have not actually been measured for any harbor porpoise population. Because a reliable estimate of 

the maximum net productivity rate is not available for Monterey Bay harbor porpoise, we use the default 

maximum net productivity rate (RMAX) of 4% for cetaceans (Wade and Angliss 1997). 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum 

population size (1,149) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times

a recovery factor of 0.45 (or a stock of unknown status with a mortality rate CV ≥0.60 and ≤0.80 ; Wade 

and Angliss 1997), resulting in a PBR of 10. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

 The incidental capture of Monterey Bay harbor porpoise is largely limited to the halibut angel 

shark set gillnet fishery. Detailed information on this fishery is provided in Appendix 1. A summary of 

estimated fishery mortality and injury for this stock of harbor porpoise for 1998-2002 is given in Table 1. 

Mortality estimates for 1998 are based on total estimated fishing effort and prior-year entanglement rate 

data (Julian and Beeson 1998), because no observer program was in place that year. Mortality estimates for 

1999-2001 are based on a National Marine Fisheries Service monitoring program in Monterey Bay 

(Cameron and Forney 2000, Carretta 2001; Carretta 2002, Carretta and Chivers 2003). 

 

Table 1. Summary of available on incidental mortality and injury of harbor porpoise (central CA stock 

1997-98; Monterey Bay stock 1999-2002) in commercial fisheries that might take this species (Cameron 

and Forney 2000, Carretta 2001, Carretta 2002, Forney et al., 2001). Mean annual takes are based on 

2001-2002 data because of fishery restrictions implemented in late 2000. n/a indicates that data are not 

available. 

Fishery Name Year(s) Data Type

Percent 

Observer 

Coverage

Observed

Mortality Kill/Day

Estimated 

Mortality 

(CV in 

parentheses)

Mean Annual Takes

(CV in parentheses)

CA angel shark / 

halibut and other 

species large mesh 

(>3.5") set gillnet 

fishery

1998 

1999 

2000 

2001 

2002

1990-94 

observer data

observer 

data 

2000 observer 

data 

Fishery closed 

permanently

0% 

23.0% 

27.0% 

0% 

0%

- 

- 

282

7 

- 

-

- 

- 

0.17 

0.10 

0.10 

0.10

57 (0.19) 

133 (0.23)2

26 (0.50) 

3 (0.77) 

16 (0.77)

 9.5 (0.66)1

Minimum total annual takes 9.5 (0.66)1

1

Only 2001-2002 mortality estimates are included in the average because the fishery was largely closed under emergency regulations 

in September 2000. The closure was made permanent in September 2002. 2

 This includes one unidentified cetacean that was almost certainly a harbor porpoise; without this animal the mortality estimate would 

be 128 (CV=0.23). 

58
All central California nearshore gill and trammel net fisheries were restricted by a series of 

emergency closures beginning in September 2000, because of concern over mortality of Common Murres 

and a decline in the southern sea otter population. During the emergency closures, fishing was prohibited 

in waters less than 60 fathoms in the region of the Monterey Bay harbor porpoise stock. There were an 

estimated 156 days of set gillnet fishing effort in Monterey Bay in 2002 following a brief lapse in the 

closure prior to a ban on set gillnets in this region on September 4, 2002. The ban is expected to virtually 

eliminate bycatch of Monterey Bay harbor porpoise in these gillnet fisheries, because this species is 

primarily found in waters shallower than 60 fathoms. Although mortality estimates for the most recent 

five years (1998-2002) are presented in Table 1, average annual takes in the setnet fishery are estimated 

using 2001-2002 data, because the fishery was largely closed under emergency regulations after September 

2000. The closure was made permanent in September 2002. An annual average of 9.5 harbor porpoise 

(CV= 0.66) were killed in this fishery in Monterey Bay from 2001-2002. 

 Twelve fishery-related stranding mortalities of harbor porpoise were documented within the range 

of the Monterey Bay harbor porpoise stock between 1998 and 2002: 1998(1); 1999(2); 2000 (2); 2001 (2) 

and 2002 (5). The five strandings in 2002 occurred during March and April, prior to a September ban on 

gillnets inshore of 60 fathoms in this region. These mortalities probably originated from the halibut set 

gillnet fishery in Monterey Bay, and are thus accounted for in the mortality estimates for this fishery. 

STATUS OF STOCK

 Harbor porpoise in California are not listed as threatened or endangered under the Endangered 

Species Act nor as depleted under the Marine Mammal Protection Act. Barlow and Hanan (1995) calculate 

the status of harbor porpoise relative to historic carrying capacity (K) using a technique called backprojection. They calculate that the central California population could have been reduced to between 30% 

and 97% of K by incidental fishing mortality, depending on the choice of input parameters. They conclude 

that there is no practical way to reduce the range of this estimate. New information does not change this 

conclusion, and the status of harbor porpoise relative to their Optimum Sustainable Population (OSP) levels 

in central California must be treated as unknown. 

 The annual mortality for 2001, after implementation of the emergency closure for central 

California gillnet fisheries, was 9.5 harbor porpoise, which is less than the calculated PBR (10) for 

Monterey Bay harbor porpoise; therefore, the Monterey Bay harbor porpoise population is not considered 

“strategic” under the MMPA. A permanent set gillnet closure inside of 60 fathoms was implemented in 

September 2002, effectively eliminating set gillnets from most harbor porpoise habitat in the region of this 

stock. This is expected to virtually eliminate gillnet mortality of Monterey Bay harbor porpoise. Although 

in recent years the average fishery mortality exceeded the PBR and, therefore, cannot be considered to be 

insignificant and approaching zero mortality and injury rate, it is likely that this goal will be met following 

the 2002 permanent gillnet closure. Research activities will continue to monitor the population size and to 

investigate population trends. There are no known habitat issues that are of particular concern for this 

stock. 

REFERENCES

Barlow, J. 1988. Harbor porpoise (Phocoena phocoena) abundance estimation in California, Oregon and 

Washington: I. Ship surveys. Fish. Bull. 86:417-432. 

Barlow, J. and P. Boveng. 1991. Modeling age-specific mortality for marine mammal populations. Mar. 

Mamm. Sci. 7(1):84-119. 

Barlow, J. and K. A. Forney. 1994. An assessment of the 1994 status of harbor porpoise in California. 

U.S. Dep. Commer., NOAA Tech. Memo. NMFS-SWFSC-205. 17 pp. 

Barlow, J. and D. Hanan. 1995. An assessment of the status of harbor porpoise in central California. 

Rept. Int. Whal., Special Issue 16:123-140. 

Calambokidis, J. and J. Barlow. 1991. Chlorinated hydrocarbon concentrations and their use for 

describing population discreteness in harbor porpoises from Washington, Oregon, and California. 

pp. 101-110 In: J. E. Reynolds III and D. K. Odell (eds.) Marine mammal strandings in the United 

States. NOAA Tech. Rep. NMFS 98. 

Carretta, J.V. 2001. Preliminary estimates of cetacean mortality in California gillnet fisheries for 2000. 

Paper SC/53/SM9 presented to the International Whaling Commission (unpublished). 21 pp. 

Carretta, J.V. 2002. Preliminary estimates of cetacean mortality in California gillnet fisheries for 2001. 

Paper SC/54/SM12 presented to the International WhalingCommission(unpublished). 22pp. 

59
Carretta, J.V. and S.J. Chivers. 2003. Preliminary estimates of marine mammal mortality and biological 

sampling of cetaceans in California gillnet fisheries for 2002. Paper SC/55/SM3 presented to the 

International Whaling Commission (unpublished). 21pp. 

Carretta, J.V., Barlow, J., K.A. Forney, M.M. Muto, and J. Baker. 2001a. U.S. Pacific Marine Mammal 

Stock Assessments: 2001. U.S. Dep. Commer. NOAA Technical Memorandum NMFS-SWFSC317. 280pp. 

Carretta, J.V., B.L. Taylor, and S.J. Chivers. 2001b. Abundance and depth distribution of harbor porpoise 

(Phocoena phocoena) in northern California determined from a 1995 ship survey. U.S. Fishery 

Bulletin 99:29-39. 

Carretta, J.V. 2003. Preliminary estimates of harbor porpoise abundance in California from 1997 and 1999 

aerial surveys. Southwest Fisheries Science Center Administrative Report LJ-03-04. 12 p. 

Carretta, J.V. and K.A. Forney. 2004. Preliminary estimates of harbor porpoise abundance in California 

from 1999 and 2002 aerial surveys. SWFSC Administrative Report LJ-04-01, available from 

Southwest Fisheries Science Center, 8604 La Jolla Shores Drive, La Jolla, CA, USA. 13pp. 

Chivers, S.J., A.E. Dizon, P.J. Gearin, and K.M. Robertson. 2002. Small-scale population structure of 

eastern North Pacific harbour porpoises, (Phocoena phocoena), indicated by molecular genetic 

analyses. Journal of Cetacean Research and Management 4(2):111-122. 

Forney, K. A. 1999a. The abundance of California harbor porpoise estimated from 1993-97 aerial linetransect surveys. Admin. Rep. LJ-99-02. Southwest Fisheries Center, National Marine Fisheries 

Service, P.O. Box 271, La Jolla, CA 92038. 16 pp. 

Forney, K. A. 1999b. Trends in harbor porpoise abundance off central California, 1986-95: Evidence for 

interannual changes in distribution? J. Cetacean Res. Manage. 1:73-80. 

Gaskin, D. E. 1984. The harbour porpoise (Phocoena phocoena L.): regional populations, status, and 

information on direct and indirect catches. Rep. int. Whal. Commn 34:569_586. 

Green, G. A., J. J. Brueggeman, R. A. Grotefendt, C. E. Bowlby, M. L. Bonnell, and K. C. Balcomb, III. 

1992. Cetacean distribution and abundance off Oregon and Washington, 1989-1990. Ch. 1 In: J. 

J. Brueggeman (ed.). Oregon and Washington Marine Mammal and Seabird Surveys. Minerals 

Management Service Contract Report 14-12-0001-30426 prepared for the Pacific OCS Region. 

Laake, J. L., J. C. Calambokidis, S. D. Osmek, and D. J. Rugh. 1997. Probability of detecting harbor 

porpoise from aerial surveys: estimating g(0). J. Wildl. Manag. 61:63-75. 

NMFS, Southwest Fisheries Science Center, P.O. Box 271, La Jolla, CA 92038-0271 

NMFS, Southwest Region, 501 West Ocean Blvd, Long Beach, CA 90802_4213 

Polacheck, T., F. W. Wenzel, and G. Early. 1995. What do stranding data say about harbor porpoise 

(Phocoena phocoena). Rep. Int. Whal. Comm., Special Issue 16:169-179. 

Rosel, P. E. 1992. Genetic population structure and systematic relationships of some small cetaceans 

inferred from mitochondrial DNA sequence variation. Ph.D. Dissertation, Univ. Calif. San Diego. 

191pp. 

Rosel, P. E., A. E. Dizon, and M. G. Haygood. 1995. Variability of the mitochondrial control region in 

populations of the harbour porpoise, Phocoena phocoena, on inter-oceanic and regional scales. 

Can. J. Fish. and Aquat. Sci. 52:1210-1219. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the 

GAMMS Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. 

Memo. NMFS-OPR-12. 93 pp. 

Woodley, T. H. and A. J. Read. 1991. Potential rates of increase of a harbour porpoise (Phocoena 

phocoena) population subjected to incidental mortality in commercial fisheries. Can. J. Fish. 

Aquat. Sci. 48:2429-2435. 

60
Revised 03/15/2005 

HARBOR PORPOISE (Phocoena phocoena): 

San Francisco-Russian River Stock

STOCK DEFINITION AND GEOGRAPHIC

RANGE

In the Pacific, harbor porpoise are found

in coastal and inland waters from Point

Conception, California to Alaska and across to

Kamchatka and Japan (Gaskin 1984). Harbor

porpoise appear to have more restricted movements 

along the western coast of the continental U.S. than

along the eastern coast. Regional differences in 

pollutant residues in harbor porpoise indicate that 

they do not move extensively between California, 

Oregon, and Washington (Calambokidis and 

Barlow 1991). That study also showed some

regional differences within California (although the 

sample size was small). This pattern stands as a 

sharp contrast to the eastern coast of the U.S. and 

Canada where harbor porpoise are believed to

migrate seasonally from as far south as the

Carolinas to the Gulf of Maine and Bay of Fundy

(Polacheck et al. 1995). A phylogeographic

analysis of genetic data from northeast Pacific

harbor porpoise did not show complete

concordance between DNA sequence types and 

geographic location (Rosel 1992). However, an

analysis of molecular variance (AMOVA) of the 

same data with additional samples found

significant genetic differences for four of the six

pair-wise comparisons between the four areas

investigated: California, Washington, British

Columbia, and Alaska (Rosel et al. 1995). These

results demonstrate that harbor porpoise along the

west coast of North America are not panmictic or 

migratory, and movement is sufficiently restricted

that genetic differences have evolved. Recent preliminary genetic analyses of samples ranging from

Monterey Bay, California to Vancouver Island, British Columbia indicate that there is small-scale

subdivision within the U.S. portion of this range (Chivers et al., 2002). 

W128.0 W126.0 W124.0 W122.0 W120.0 W118.0

N34.0

N36.0

N38.0

N40.0

N42.0

N44.0

Oregon

California Northern California/

Southern Oregon

San FranciscoRussian River

Monterey

 Bay

Morro Bay

Cape Blanco

Monterey Bay

Cape Mendocino

Point Conception

Point Arena

Morro Bay

Oregon/Washington

 coast

Russian River

Figure 1. Stock boundaries and distributional

range of harbor porpoise along the California and 

southern Oregon coast. Shaded area represents

harbor porpoise habitat (0-200 m) along the U.S.

west coast.

In their assessment of harbor porpoise, Barlow and Hanan (1995) recommended that the animals 

inhabiting central California (defined to be from Point Conception to the Russian River) be treated as a

separate stock. Their justifications for this were: 1) fishery mortality of harbor porpoise is limited to

central California, 2) movement of individual animals appears to be restricted within California, and 

consequently 3) fishery mortality could cause the local depletion of harbor porpoise if central California is

not managed separately. Although geographic structure exists along an almost continuous distribution of 

harbor porpoise from California to Alaska, stock boundaries are difficult to draw because any rigid line is

(to a greater or lesser extent) arbitrary from a biological perspective. Nonetheless, failure to recognize 

geographic structure by defining management stocks can lead to depletion of local populations. Based on

recent genetic findings (Chivers et al., 2002), California coast stocks were re-evaluated, and significant

genetic differences were found among 4 identified sampling sites. Revised stock boundaries are presented

here based on these genetic data and density discontinuities identified from aerial surveys, resulting in six

California/Oregon/Washington stocks where previously there had been four (Carretta et al. 2001a). The 

stock boundaries for animals that occur in California/southern Oregon waters are shown in Figure 1. For

the 2002 Marine Mammal Protection Act (MMPA) Stock Assessment Reports, other Pacific coast harbor

61
porpoise stocks include: 1) a Morro Bay stock, 2) a Monterey Bay stock, 3) a northern California/southern

Oregon stock, 4) an Oregon/Washington coast stock, 5) an Inland Washington stock, 6) a Southeast Alaska

stock, 7) a Gulf of Alaska stock, and 8) a Bering Sea stock. Stock assessment reports for Morro Bay,

Monterey Bay, northern California/southern Oregon, Oregon/Washington coast, and Inland Washington

waters harbor porpoise appear in this volume. The three Alaska harbor porpoise stocks are reported 

separately in the Stock Assessment Reports for the Alaska Region. 

POPULATION SIZE

Previous estimates of abundance for California harbor porpoise were based on aerial surveys 

conducted between the coast and the 50-fm isobath during 1988-95 (Barlow and Forney 1994, Forney

1999a). These estimates did not include an unknown number of animals found in deeper waters. Barlow

(1988) found that the vast majority of harbor porpoise in California were within the 0-50-fm depth range;

however, Green et al. (1992) found that 24% of harbor porpoise seen during aerial surveys of Oregon and 

Washington were between the 100m and 200m isobaths (55 to 109 fathoms). A systematic ship survey of

depth strata out to 90 m in northern California showed that porpoise abundance declined significantly in

waters deeper than 60 m (Carretta et al. 2001b). A recent analysis of harbor porpoise trends including 

oceanographic data suggests that the proportion of California harbor porpoise in deeper waters may vary

between years (Forney 1999b). In 1999 and 2002, aerial surveys extended farther offshore (to the 200m 

depth contour or a minimum of 15 nmi from shore in the region of the San Francisco-Russian River stock)

to provide a more complete abundance estimate. Although two harbor porpoise sightings were made in

offshore waters under poor conditions (Beaufort sea state 3), only good conditions have traditionally been 

included in abundance analyses for this species (Barlow and Forney 1994, Forney 1999a), and therefore no

offshore sightings contributed to the abundance estimate for this stock. Based on 1999-2002 aerial surveys

under good survey conditions (Beaufort ≤2, cloud cover ≤25%) the estimate of abundance for this stock is

8,521 animals (CV = 0.38) (Carretta and Forney 2004).

 

Minimum Population Estimate

The minimum population estimate for the San Francisco-Russian River harbor porpoise stock is

taken as the lower 20th percentile of the log-normal distribution of the abundance estimated from 1999-

2002 aerial surveys, or 6,254 animals. 

Current Population Trend

Analyses of a 1986-95 time series of aerial surveys have been conducted to examine trends in harbor 

porpoise abundance in central California (Forney, 1995; 1999b). After controlling for the effects of sea

state, cloud cover, and area on

sighting rates, Forney (1995) 

found a negative trend in

population size; however, that

trend was no longer significant 

when sea surface temperature (a 

proxy measure of oceanographic

conditions) was included in an 

updated non-linear trend analysis

(Forney 1999b). The negative 

correlation between harbor

porpoise sighting rates and sea

surface temperatures indicates 

that apparent trends could be 

caused by changing 

oceanographic conditions and 

movement of animals into and

out of the study area. Encounter 

rates for the 1997 survey, 

however, were very high (Forney

1999a) despite the warmer sea

Figure 2. Aerial survey estimates of abundance for the San 

Fr o-Russian River stock of harbor porpoise, 1988-2002. 

Er o rs represent lower and upper 95% confidence intervals. 

So e represents a linear regression of the natural logarithm of

a n ce over time. The slope of this regression is not

statistically significant (p = 0.24). 

ancisc

r r ba

lid lin

bu dan

San Francisco - Russian River

0

5000

10000

15000

20000

25000

198819891990199119921993199419951996199719981999200020012002

Year

Porpoise Abundance

Figure 2. Aerial survey estimates of abundance for the San 

Francisco-Russian River stock of harbor porpoise, 1988-2002. 

Error bars represent lower and upper 95% confidence intervals.

Solid line represents a linear regression of the natural logarithm of

abundance over time. The slope of this regression line is not 

statistically significant (p=0.24). 

62
surface temperatures caused by strong El Niño conditions. These observations suggest that patterns of 

harbor porpoise movement are not directly related to sea surface temperature, but rather to the more 

complex distribution of potential prey species in this area. Abundance of the San Francisco - Russian 

River harbor porpoise stock appeared to be stable or declining between 1988-1991 and has steadily 

increased since 1993. The slope of the linear regression on the natural logarithm of abundance over time is 

not statistically significant (p = 0.24, Figure 2). More detailed studies of encounter rate patterns in relation 

to satellite-derived sea surface temperature are planned to shed light on potential oceanography-related 

movement patterns of harbor porpoise in this region. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 Based on what are argued to be biological limits of the species (i.e. females give birth first at age 4 

and produce one calf per year until death), the theoretical, maximum-conceivable growth rate of a closed 

harbor porpoise population was estimated as 9.4% per year (Barlow and Boveng 1991). This maximum 

theoretical rate may not be achievable for any real population. [Woodley and Read (1991) calculate a 

maximum growth rate of approximately 5% per year, but their argument for this being a maximum (i.e. that 

porpoise survival rates cannot exceed those of Himalayan thar) is not well justified.] Population growth 

rates have not actually been measured for any harbor porpoise population. Because a reliable estimate of 

the maximum net productivity rate is not available for northern California harbor porpoise, we use the 

default maximum net productivity rate (RMAX) of 4% for cetaceans (Wade and Angliss 1997). 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum 

population size (6,254) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times

a recovery factor of 0.5 (for a species of unknown status; Wade and Angliss 1997), resulting in a PBR of 

63. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

 The incidental capture of harbor porpoise in California has largely been limited to set gillnet 

fisheries in Monterey Bay and to a lesser extent, Morro Bay. Coastal setnets are not allowed north of 

Bodega Head (to protect salmon resources there). However, two harbor porpoise strandings near Bodega 

Head in 1998, one inside San Francisco Bay in 1998, and one near Montara, San Mateo County in 2001 

were attributed to fishery-related mortality, but the responsible fishery is unknown. Although the stranding 

locations fall within the range of the San Francisco-Russian River harbor porpoise stock and this is 

probably the source stock for the mortalities, it is possible that some of these animals were taken from the 

northern California/southern Oregon stock and subsequently drifted southward to the stranding location. A 

ban on set gillnets inshore of 60 fathoms from Point Reyes south to Point Arguello, California has been in 

place since September 2002. 

Table 1. Summary of available information on incidental mortality and injury of harbor porpoise (San 

Francisco-Russian River stock) in commercial fisheries that might take this species. Mean annual takes are 

based on 1998-2002 data unless noted otherwise. n/a indicates that data are not available. 

Fishery Name Year(s) Data 

Type

Percent 

Observer 

Coverage

Observed 

Mortality

Kill/Day Estimated 

Mortality (CV in 

parentheses)

Mean Annual 

Takes (CV in 

parentheses)

Unknown 

fishery 1998-2002

stranding n/a 3 (in 1998) 

1 in 2001

n/a

≥0.8 (n/a)

Minimum total annual takes

≥0.8 (n/a)

STATUS OF STOCK

 Harbor porpoise in California are not listed as threatened or endangered under the Endangered 

Species Act nor as depleted under the Marine Mammal Protection Act. Barlow and Hanan (1995) calculate 

the status of harbor porpoise relative to historic carrying capacity (K) using a technique called backprojection. They calculate that the central California population (including Morro Bay, Monterey Bay, and 

63
San Francisco-Russian River stocks) could have been reduced to between 30% and 97% of K by incidental 

fishing mortality, depending on the choice of input parameters. They conclude that there is no practical 

way to reduce the range of this estimate. New information does not change this conclusion, and the status 

of central California harbor porpoise populations relative to their Optimum Sustainable Population (OSP) 

levels must be treated as unknown. There are no known habitat issues that are of particular concern for this 

stock. Because the known human-caused mortality or serious injury (0.8 harbor porpoise per year) is less 

than the PBR (63), this stock is not considered a "strategic" stock under the MMPA. Because average 

annual fishery mortality is less than 10% of the PBR, the fishery mortality can be considered insignificant 

and approaching zero mortality and serious injury rate. 

REFERENCES

Barlow, J. 1988. Harbor porpoise (Phocoena phocoena) abundance estimation in California, Oregon and 

Washington: I. Ship surveys. Fish. Bull. 86:417-432. 

Barlow, J. and P. Boveng. 1991. Modeling age-specific mortality for marine mammal populations. Mar. 

Mamm. Sci. 7(1):84-119. 

Barlow, J. and K. A. Forney. 1994. An assessment of the 1994 status of harbor porpoise in California. 

U.S. Dep. Commer., NOAA Tech. Memo. NMFS-SWFSC-205. 17 pp. 

Barlow, J. and D. Hanan. 1995. An assessment of the status of harbor porpoise in central California. 

Rept. Int. Whal., Special Issue 16:123-140. 

Calambokidis, J. and J. Barlow. 1991. Chlorinated hydrocarbon concentrations and their use for 

describing population discreteness in harbor porpoises from Washington, Oregon, and California. 

pp. 101-110 In: J. E. Reynolds III and D. K. Odell (eds.) Marine mammal strandings in the United 

States. NOAA Tech. Rep. NMFS 98. 

Carretta, J.V., J. Barlow, K.A. Forney, M.M. Muto, and J. Baker. 2001a. U.S. Pacific Marine Mammal 

Stock Assessments: 2001. U.S. Dep. Commer. NOAA Technical Memorandum, NOAA-TMNMFS-SWFSC-317. 280 p. 

Carretta, J.V., B.L. Taylor, and S.J. Chivers. 2001b. Abundance and depth distribution of harbor porpoise 

(Phocoena phocoena) in northern California determined from a 1995 ship survey. U.S. Fishery 

Bulletin 99:29-39. 

Carretta, J.V. 2003. Preliminary estimates of harbor porpoise abundance in California from 1997 and 1999 

aerial surveys. Southwest Fisheries Science Center Administrative Report LJ-03-04. 12 p. 

Carretta, J.V. and K.A. Forney. 2004. Preliminary estimates of harbor porpoise abundance in California 

from 1999 and 2002 aerial surveys. SWFSC Administrative Report LJ-04-01, available from 

Southwest Fisheries Science Center, 8604 La Jolla Shores Drive, La Jolla, CA, USA. 13pp. 

Chivers, S.J., A.E. Dizon, P.J. Gearin, and K.M. Robertson. 2002. Small-scale population structure of 

eastern North Pacific harbour porpoises, (Phocoena phocoena), indicated by molecular genetic 

analyses. Journal of Cetacean Research and Management 4(2):111-122. 

Forney, K. A. 1999a. The abundance of California harbor porpoise estimated from 1993-97 aerial linetransect surveys. Admin. Rep. LJ-99-02. Southwest Fisheries Center, National Marine Fisheries 

Service, P.O. Box 271, La Jolla, CA 92038. 16 pp. 

Forney, K. A. 1999b. Trends in harbor porpoise abundance off central California, 1986-95: Evidence for 

interannual changes in distribution? J. Cetacean Res. Manage. 1:73-80. 

Gaskin, D. E. 1984. The harbour porpoise (Phocoena phocoena L.): regional populations, status, and 

information on direct and indirect catches. Rep. int. Whal. Commn 34:569_586. 

Green, G. A., J. J. Brueggeman, R. A. Grotefendt, C. E. Bowlby, M. L. Bonnell, and K. C. Balcomb, III. 

1992. Cetacean distribution and abundance off Oregon and Washington, 1989-1990. Ch. 1 In: J. 

J. Brueggeman (ed.). Oregon and Washington Marine Mammal and Seabird Surveys. Minerals 

Management Service Contract Report 14-12-0001-30426 prepared for the Pacific OCS Region. 

Laake, J. L., J. C. Calambokidis, S. D. Osmek, and D. J. Rugh. 1997. Probability of detecting harbor 

porpoise from aerial surveys: estimating g(0). J. Wildl. Manag. 61:63-75. 

NMFS, Southwest Fisheries Science Center, P.O. Box 271, La Jolla, CA 92038-0271. 

NMFS, Southwest Region, 501 West Ocean Blvd, Long Beach, CA 90802-4213 

Polacheck, T., F. W. Wenzel, and G. Early. 1995. What do stranding data say about harbor porpoise 

(Phocoena phocoena). Rep. Int. Whal. Comm., Special Issue 16:169-179. 

64
Rosel, P. E. 1992. Genetic population structure and systematic relationships of some small cetaceans 

inferred from mitochondrial DNA sequence variation. Ph.D. Dissertation, Univ. Calif. San Diego. 

191pp. 

Rosel, P. E., A. E. Dizon, and M. G. Haygood. 1995. Variability of the mitochondrial control region in 

populations of the harbour porpoise, Phocoena phocoena, on inter-oceanic and regional scales. 

Can. J. Fish. and Aquat. Sci. 52:1210-1219. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the 

GAMMS Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. 

Memo. NMFS-OPR-12. 93 pp. 

Woodley, T. H. and A. J. Read. 1991. Potential rates of increase of a harbour porpoise (Phocoena 

phocoena) population subjected to incidental mortality in commercial fisheries. Can. J. Fish. 

Aquat. Sci. 48:2429-2435. 

65
Revised 10/31/2002 

HARBOR PORPOISE (Phocoena phocoena): 

Northern California/Southern Oregon Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

In the Pacific, harbor porpoise are found

in coastal and inland waters from Point

Conception, California to Alaska and across to

Kamchatka and Japan (Gaskin 1984). Harbor

porpoise appear to have more restricted movements 

along the western coast of the continental U.S. than

along the eastern coast. Regional differences in 

pollutant residues in harbor porpoise indicate that 

they do not move extensively between California, 

Oregon, and Washington (Calambokidis and 

Barlow 1991). That study also showed some

regional differences within California (although the 

sample size was small). This pattern stands as a 

sharp contrast to the eastern coast of the U.S. and 

Canada where harbor porpoise are believed to

migrate seasonally from as far south as the

Carolinas to the Gulf of Maine and Bay of Fundy

(Polacheck et al. 1995). A phylogeographic 

analysis of genetic data from northeast Pacific

harbor porpoise did not show complete

concordance between DNA sequence types and 

geographic location (Rosel 1992). However, an

analysis of molecular variance (AMOVA) of the 

same data with additional samples found

significant genetic differences for four of the six

pair-wise comparisons between the four areas

investigated: California, Washington, British

Columbia, and Alaska (Rosel et al. 1995). These

results demonstrate that harbor porpoise along the

west coast of North America are not panmictic or 

migratory, and movement is sufficiently restricted

that genetic differences have evolved. Recent

preliminary genetic analyses of samples ranging

from Monterey Bay, California to Vancouver

Island, British Columbia indicate that there is small-scale subdivision within the U.S. portion of this range

Chivers et al., in press). 

W128.0 W126.0 W124.0 W122.0 W120.0 W118.0

N34.0

N36.0

N38.0

N40.

N42.

N44.

0

0

0

Oregon

California Northern California/

Southern Oregon

San FranciscoRussian River

Monterey

 Bay

Morro Bay

Cape Blanco

Monterey Bay

Cape Mendocino

Point Conception

Point Arena

Morro Bay

Oregon/Washington

 coast

Russian River

Figure 1. Stock boundaries and distributional

range of harbor porpoise along the 

California/southern Oregon coast. Shaded area

represents harbor porpoise habitat (0-200 m)

along the U.S. west coast.

In their assessment of harbor porpoise, Barlow and Hanan (1995) recommended that the animals 

inhabiting central California (defined to be from Point Conception to the Russian River) be treated as a

separate stock. Their justifications for this were: 1) fishery mortality of harbor porpoise is limited to

central California, 2) movement of individual animals appears to be restricted within California, and 

consequently 3) fishery mortality could cause the local depletion of harbor porpoise if central California is

not managed separately. Although geographic structure exists along an almost continuous distribution of 

harbor porpoise from California to Alaska, stock boundaries are difficult to draw because any rigid line is

(to a greater or lesser extent) arbitrary from a biological perspective. Nonetheless, failure to recognize 

geographic structure by defining management stocks can lead to depletion of local populations. Based on

recent genetic findings (Chivers et al., in press), California coast stocks were re-evaluated and significant 

genetic differences were found among four identified sampling sites. Revised stock boundaries are 

presented here based on these genetic data and density discontinuities identified from aerial surveys, 

resulting in six west coast stocks where previously there had been four (Carretta et al. 2001a). These new

stock boundaries are shown in Figure 1. For the 2002 Marine Mammal Protection Act (MMPA) Stock 

66
Assessment Reports, other Pacific coast harbor porpoise stocks include: 1) a Morro Bay stock, 2) a

Monterey Bay stock, 3) a San Francisco-Russian River stock, 4) an Oregon/Washington coast stock, 5) an

Inland Washington stock, 6) a Southeast Alaska stock, 7) a Gulf of Alaska stock, and 8) a Bering Sea 

stock. The stock assessment reports for Morro Bay, Monterey Bay, and San Francisco-Russian River,

harbor porpoise appear in this volume. The three Alaska harbor porpoise stocks are reported separately in

the Stock Assessment Reports for the Alaska Region. 

POPULATION SIZE

Previous estimates of abundance for California harbor porpoise were based on aerial surveys 

conducted between the coast and the 50-fm isobath during 1988-95 (Barlow and Forney 1994, Forney

1999a). These estimates did not include an unknown number of animals found in deeper waters. Barlow

(1988) found that the vast majority of harbor porpoise in California were within the 0-50-fm depth range;

however, Green et al. (1992) found that 24% of harbor porpoise seen during aerial surveys of Oregon and 

Washington were between the 100m and 200m isobaths (55 to 109 fathoms). A systematic ship survey of

depth strata out to 90 m in northern California showed that porpoise abundance declined significantly in

waters deeper than 60 m (Carretta et al. 2001b). A recent analysis of harbor porpoise trends including 

oceanographic data suggests that the proportion of California harbor porpoise in deeper waters may vary

between years (Forney 1999b; see Current Population Trend below). In 1999, aerial surveys extended 

farther offshore (to the 200m depth contour or 15 nmi distance, whichever is farther) to provide a more

complete abundance estimate. Based on pooled 1997-99 aerial survey data including data from both

inshore and offshore areas, an updated estimate of abundance for the northern California/southern Oregon 

harbor porpoise stock is 17,763 harbor porpoise (CV=0.39). Approximately 1,572 (CV=0.86) porpoise 

were estimated in the northern California offshore stratum (SWFSC, unpublished data); 11,135 (CV= 0.38) 

in the northern California inshore stratum (SWFSC, unpublished data); 4,808 (CV = 0.49) from southern

Oregon Area VI (Laake et al. 1998), and 250 (CV = 1.09) animals from southern Oregon Area VIF (Laake 

et al. 1998). 

Minimum Population Estimate

The minimum population

estimate for harbor porpoise in

northern California/southern

Oregon is taken as the lower 20th

percentile of the log-normal

distribution of the abundance

estimated from 1997-99 aerial

surveys in northern California and

1997 aerial surveys in southern 

Oregon, or 12,940 animals. This

estimate includes harbor porpoise

within an area extending to the 

200m isobath or 15 nmi,

whichever is farther from shore. 

Current Population Trend

mines

nds i

Forney (1999b) exa

tre n relative harbor porpoise 

abundance in central and northern 

California based on aerial surveys

from 1989-95. No significant

trends were evident over this time

period for the Northern California Stock. The 1997-99 survey results continue to show no trend in relative 

abundance (Figure 2). 

0.00

0.20

0.40

0.60

0.80

1.00

1.20

Relative abundance (porpoise/km)

87 89 91 93 95 97 99

Year

Figure 2. Relative abundance (+/- one standard error) of central 

California (Pt. Conception to Russian River) harbor porpoise, 

1986-99, adjusted for sea state and cloud cover (following 

methods of Forney 1995). The trend shown includes the range of

three California stocks (Morro Bay, Monterey Bay, and SanFrancisco-Russian River. 

67
CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 Based on what are argued to be biological limits of the species (i.e. females give birth first at age 4 

and produce one calf per year until death), the theoretical, maximum-conceivable growth rate of a closed 

harbor porpoise population was estimated as 9.4% per year (Barlow and Boveng 1991). This maximum 

theoretical rate may not be achievable for any real population. [Woodley and Read (1991) calculate a 

maximum growth rate of approximately 5% per year, but their argument for this being a maximum (i.e. that 

porpoise survival rates cannot exceed those of Himalayan thar) is not well justified.] Population growth 

rates have not actually been measured for any harbor porpoise population. Because a reliable estimate of 

the maximum net productivity rate is not available for northern California harbor porpoise, we use the 

default maximum net productivity rate (RMAX) of 4% for cetaceans (Wade and Angliss 1997). 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum 

population size (12,940) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times

a recovery factor of 1.0 (for a species within its Optimal Sustainable Population; Wade and Angliss 1997), 

resulting in a PBR of 259. 

HUMAN-CAUSED MORTALITY

Fishery Information

 The incidental capture of harbor porpoise in California is largely limited to set gillnet fisheries in 

central California. Coastal setnets are not allowed in northern California (to protect salmon resources 

there). However, one harbor porpoise mortality was documented for the Klamath River tribal salmon 

gillnet fishery in 1995 (NMFS, Southwest Region, unpublished data). There have been no observed harbor 

porpoise mortalities or fishery-related strandings in the Klamath River tribal salmon gillnet fishery for the 

most recent five-year period (1996-2000) (pers. comm., Kathleen Williamson, Yurok tribe biologist). 

Table 1. Summary of available information on incidental mortality and injury of harbor porpoise (northern 

CA stock) in fisheries that might take this species. n/a indicates that data are not available. 

Fishery Name Year(s) Data Type

Percent 

Observer 

Coverage

Observed 

Mortality

Estimated Mortality 

(CV in parentheses)

Mean Annual Takes 

(CV in parentheses)

CA Klamath River tribal 

salmon gillnet fishery

1996-

2000 Observation n/a 0 0 0

Minimum total annual takes

0

 

STATUS OF STOCK

 Harbor porpoise in northern California/southern Oregon are not listed as threatened or endangered 

under the Endangered Species Act nor as depleted under the Marine Mammal Protection Act. There are no 

known habitat issues that are of particular concern for this stock. Because of the lack of recent or historical 

sources of human-caused mortality, the harbor porpoise stock in northern California has been concluded to 

be within their Optimum Sustainable Population (OSP) level (Barlow and Forney 1994). Because the 

known human-caused mortality or serious injury (0 harbor porpoise per year) is less than the PBR (259), 

this stock is not considered a "strategic" stock under the MMPA. Because average annual fishery mortality 

is less than 10% of the PBR, the fishery mortality can be considered insignificant and approaching zero 

mortality and serious injury rate. 

REFERENCES

Barlow, J. 1988. Harbor porpoise (Phocoena phocoena) abundance estimation in California, Oregon and 

Washington: I. Ship surveys. Fish. Bull. 86:417-432. 

Barlow, J. and P. Boveng. 1991. Modeling age-specific mortality for marine mammal populations. Mar. 

Mamm. Sci. 7(1):84-119. 

Barlow, J. and K. A. Forney. 1994. An assessment of the 1994 status of harbor porpoise in California. 

U.S. Dep. Commer., NOAA Tech. Memo. NMFS-SWFSC-205. 17 pp. 

68
Barlow, J. and D. Hanan. 1995. An assessment of the status of harbor porpoise in central California. 

Rept. Int. Whal., Special Issue 16:123-140. 

Carretta, J.V. J. Barlow, K.A. Forney, M.M. Muto, and J. Baker. 2001a. U.S. Pacific Marine Mammal 

Stock Assessments: 2001. U.S. Dep. Commer. NOAA Technical Memorandum, NOAA-TMNMFS-SWFSC-317. 280p. 

Carretta, J.V., B.L. Taylor, and S.J. Chivers. 2001b. Abundance and depth distribution of harbor porpoise 

(Phocoena phocoena) in northern California determined from a 1995 ship survey. U.S. Fishery 

Bulletin 99:29-39. 

Calambokidis, J. and J. Barlow. 1991. Chlorinated hydrocarbon concentrations and their use for 

describing population discreteness in harbor porpoises from Washington, Oregon, and California. 

pp. 101-110 In: J. E. Reynolds III and D. K. Odell (eds.) Marine mammal strandings in the United 

States. NOAA Tech. Rep. NMFS 98. 

Chivers, S. Southwest Fisheries Science Center, NMFS, P.O. Box 271, La Jolla, CA 92038 

Forney, K. A. 1999a. The abundance of California harbor porpoise estimated from 1993-97 aerial linetransect surveys. Admin. Rep. LJ-99-02. Southwest Fisheries Center, National Marine Fisheries 

Service, P.O. Box 271, La Jolla, CA 92038. 16 pp. 

Forney, K. A. 1999b. Trends in harbor porpoise abundance off central California, 1986-95: Evidence for 

interannual changes in distribution? J. Cetacean Res. Manage. 1:73-80. 

Gaskin, D. E. 1984. The harbour porpoise (Phocoena phocoena L.): regional populations, status, and 

information on direct and indirect catches. Rep. int. Whal. Commn 34:569_586. 

Green, G. A., J. J. Brueggeman, R. A. Grotefendt, C. E. Bowlby, M. L. Bonnell, and K. C. Balcomb, III. 

1992. Cetacean distribution and abundance off Oregon and Washington, 1989-1990. Ch. 1 In: J. 

J. Brueggeman (ed.). Oregon and Washington Marine Mammal and Seabird Surveys. Minerals 

Management Service Contract Report 14-12-0001-30426 prepared for the Pacific OCS Region. 

Laake, J. L., J. C. Calambokidis, S. D. Osmek, and D. J. Rugh. 1997. Probability of detecting harbor 

porpoise from aerial surveys: estimating g(0). J. Wildl. Manag. 61:63-75. 

Laake, J., J. Calambokidis, S. Osmek. 1998. Survey report for the 1997 aerial surveys for harbor porpoise 

and other marine mammals of Oregon, Washington, and British Columbia outside waters. Alaska 

Fisheries Science Center Processed Report 98-10. pp. 77-97. 

NMFS, Southwest Fisheries Science Center, P.O. Box 271, La Jolla, CA 92038-0271 

NMFS, Southwest Region, 501 West Ocean Blvd, Long Beach, CA 90802_4213 

Polacheck, T., F. W. Wenzel, and G. Early. 1995. What do stranding data say about harbor porpoise 

(Phocoena phocoena). Rep. Int. Whal. Comm., Special Issue 16:169-179. 

Rosel, P. E. 1992. Genetic population structure and systematic relationships of some small cetaceans 

inferred from mitochondrial DNA sequence variation. Ph.D. Dissertation, Univ. Calif. San Diego. 

191pp. 

Rosel, P. E., A. E. Dizon, and M. G. Haygood. 1995. Variability of the mitochondrial control region in 

populations of the harbour porpoise, Phocoena phocoena, on inter-oceanic and regional scales. 

Can. J. Fish. and Aquat. Sci. 52:1210-1219. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the 

GAMMS Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. 

Memo. NMFS-OPR-12. 93 pp. 

Woodley, T. H. and A. J. Read. 1991. Potential rates of increase of a harbour porpoise (Phocoena 

phocoena) population subjected to incidental mortality in commercial fisheries. Can. J. Fish. 

Aquat. Sci. 48:2429-2435. 

69
Revised 12/15/2006

HARBOR PORPOISE (Phocoena phocoena): 

Oregon/Washington Coast Stock

STOCK DEFINITION AND GEOGRAPHIC RANGE

In the eastern North Pacific Ocean, harbor

porpoise are found in coastal and inland waters from Point

Barrow, along the Alaskan coast, and down the west coast 

of North America to Point Conception, California (Gaskin

1984). Harbor porpoise are known to occur year-round in

the inland trans-boundary waters of Washington and 

British Columbia, Canada (Osborne et al. 1988), and along

the Oregon/Washington coast (Barlow 1988, Barlow et al. 

1988, Green et al. 1992). Aerial survey data from coastal 

Oregon and Washington, collected during all seasons,

suggest that harbor porpoise distribution varies by depth 

(Green et al. 1992). Although distinct seasonal changes in

abundance along the west coast have been noted, and

attributed to possible shifts in distribution to deeper

offshore waters during late winter (Dohl et al. 1983, 

Barlow 1988), seasonal movement patterns are not fully

understood. 

Investigation of pollutant loads in harbor porpoise

ranging from California to the Canadian border suggests

restricted harbor porpoise movements (Calambokidis and

Barlow 1991). Stock discreteness in the eastern North 

Pacific was analyzed using mitochondrial DNA from 

samples collected along the west coast (Rosel 1992) and is

summarized in Osmek et al. (1994). Two distinct mtDNA

groupings or clades exist. One clade is present in 

California, Washington, British Columbia, and Alaska (no 

samples were available from Oregon), while the other is 

found only in California and Washington. Although these

two clades are not geographically distinct by latitude, the 

results may indicate a low mixing rate for harbor porpoise

along the west coast of North America. Further genetic

testing of the same data, along with additional samples, 

found significant genetic differences for four of the six pair-wise comparisons between the four areas investigated:

California, Washington, British Columbia, and Alaska (Rosel et al. 1995). These results demonstrate that harbor

porpoise along the west coast of North America are not panmictic or migratory and that movement is sufficiently 

restricted that genetic differences have evolved. Recent preliminary genetic analyses of samples ranging from

Monterey Bay, California, to Vancouver Island, British Columbia, indicate that there is small-scale subdivision

within the U.S. portion of this range (Chivers et al. 2002). This is consistent with low movement suggested by

genetic analysis of harbor porpoise specimens from the North Atlantic, where numerous stocks have been delineated

with clinal differences over areas as small as the waters surrounding the British Isles. 

Using th

Oregon/

Washington

Coast stock

Washington

Inland Waters

stock

Oregon

Washington

Cape Blanco

126°W

126°W

124°W 122°W 120°W

42°N

44°N

46°N

48°N

Figure 1. Stock boundaries (dashed lines) and

approximate distribution (shaded areas) of harbor

porpoise along the coasts of Washington and

northern Oregon.

e 1990-1991 aerial survey data of Calambokidis et al. (1993) for water depths <50 fathoms, Osmek

et al. (1996) found significant differences in harbor porpoise mean densities (z=5.9, p<0.01) between the waters of

coastal Oregon/Washington and inland Washington/southern British Columbia, Canada (i.e., Strait of Juan de

Fuca/San Juan Islands). Although differences in density exist between coastal Oregon/Washington and inland

Washington waters, a specific stock boundary line cannot be identified based upon biological or genetic differences.

However, harbor porpoise movements and rates of intermixing within the eastern North Pacific are restricted, and 

there has been a significant decline in harbor porpoise sightings within southern Puget Sound since the 1940s;

therefore, following a risk averse management strategy, two stocks are recognized: the Oregon/Washington Coast

stock (between Cape Blanco, OR, and Cape Flattery, WA) and the Washington Inland Waters stock (in waters east

of Cape Flattery) (see Fig. 1). Recent genetic evidence suggests that the population of eastern North Pacific harbor 

70
porpoise is more finely structured than is currently recognized (Chivers et al. 2002). All relevant data (e.g., genetic 

samples, contaminant studies, and satellite tagging) will be reviewed to determine whether to adjust the stock 

boundaries for harbor porpoise in Oregon and Washington waters. 

 In their assessment of California harbor porpoise, Barlow and Hanan (1995) recommended two stocks be 

OPULATION SIZE

September 2002, an aerial survey of Oregon, Washington, and southern British Columbia 

astal w

inimum Population Estimate

 estimate for this stock is calculated as the lower 20th percentile of the log-normal 

istribut

urrent Population Trend

e data on population trends of harbor porpoise for coastal Oregon, Washington, or 

ritish C

URRENT AND MAXIMUM NET PRODUCTIVITY RATES

 is currently not available for harbor porpoise. 

herefor

OTENTIAL BIOLOGICAL REMOVAL

R) level for this stock is calculated as the minimum population size 

7,705)

recognized in California, with the stock boundary at the Russian River. Based on recent genetic findings (Chivers et 

al. 2002), California coast stocks were re-evaluated and significant genetic differences were found among four 

identified sampling sites. Revised stock boundaries, based on these genetic data and density discontinuities 

identified from aerial surveys, resulted in six California/Oregon/Washington stocks where previously there had been 

four (Carretta et al. 2001): 1) the Washington Inland Waters stock, 2) the Oregon/Washington Coast stock, 3) the 

Northern California/Southern Oregon stock, 4) the San Francisco-Russian River stock, 5) the Monterey Bay stock, 

and 6) the Morro Bay stock. The stock boundaries for animals that occur in Washington/northern Oregon waters are 

shown in Figure 1. This report considers only the Oregon/Washington Coast stock. Stock assessment reports for 

Washington Inland Waters, Northern California/Southern Oregon, San Francisco-Russian River, Monterey Bay, and 

Morro Bay harbor porpoise also appear in this volume. Stock assessment reports for the three harbor porpoise 

stocks in the inland and coastal waters of Alaska, including 1) the Southeast Alaska stock, 2) the Gulf of Alaska 

stock, and 3) the Bering Sea stock, are reported separately in the Stock Assessment Reports for the Alaska Region. 

The harbor porpoise occurring in British Columbia have not been included in any of the U.S. stock assessment 

reports. 

P

 In August and 

co aters, from shore to 200 m depth, resulted in an uncorrected abundance estimate of 11,036 (CV=0.11) 

harbor porpoise in U.S. waters north of Cape Blanco, OR (J. Laake, unpubl. data). Using a correction factor of 3.42 

(1/g(0); g(0)=0.292, CV=0.366) (Laake et al. 1997a), to adjust for groups missed by aerial observers, the corrected 

estimate of abundance for harbor porpoise in coastal Oregon (north of Cape Blanco) and Washington waters is 

37,745 (CV=0.38). 

M

 The minimum population

d ion (Wade and Angliss 1997) of the 2002 population estimate of 37,745, which is 27,705 harbor porpoise. 

C

 There are no reliabl

B olumbia waters, however, the uncorrected estimates of abundance for the Oregon/Washington Coast stock 

in 1997 (11,599) and 2002 (11,036) were not significantly different (Z=-.31, P=0.76) (Laake et al. 1998a; J. Laake, 

unpubl. data). 

C

 A reliable estimate of the maximum net productivity rate

T e, until additional data become available, it is recommended that the cetacean maximum theoretical net 

productivity rate (RMAX) of 4% (Wade and Angliss 1997) be employed for the Oregon/Washington Coast harbor 

porpoise stock. 

P

 The potential biological removal (PB

(2 times one-half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.5 

(for a stock of unknown status, Wade and Angliss 1997), resulting in a PBR of 277 harbor porpoise per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Z boundaries of coastal Oregon and Washington, human-caused (fishery) mortalities of 

rbor p

Fisheries Information

 Within the EE

ha orpoise are presently known to occur only in the northern Washington marine set gillnet fishery. During 

1992-1993, the Washington/Oregon Lower Columbia River, Washington Grays Harbor, and Washington Willapa 

Bay drift gillnet fisheries were monitored at observer coverages of approximately 4% and 2%, respectively. There 

were no observed harbor porpoise mortalities in these fisheries. 

71
 Fishing effort in the northern Washington marine set gillnet fishery (areas 4, 4A, 4B, and 5) is conducted 

within the range of both harbor porpoise stocks (Oregon/Washington Coast and Washington Inland Waters) 

occurring in Washington State waters. Some movement of harbor porpoise between Washington’s coastal and 

inland waters is likely, but it is currently not possible to quantify the extent of such movements. For the purposes of 

this stock assessment report, the animals taken in waters south and west of Cape Flattery, WA (areas 4 and 4A), are 

assumed to have belonged to the Oregon/Washington Coast stock, and Table 1 includes data only from that portion 

of the fishery. NMFS observers monitored 100% of the 50 net days (1 net day equals a 100-fathom length net set 

for 24 hours) of fishing effort in coastal waters in 2000 and observed three harbor porpoise takes; no fishing effort 

occurred in the coastal portion of the fishery in 1999 or 2001-2003 (Gearin, et al. 1994, 2000; P. Gearin, unpubl. 

data). There has been a reduction in fishing effort in the coastal portion of this fishery due to reduced numbers of 

chinook salmon (a target species) in coastal waters. The mean estimated mortality for this fishery in 1999-2003 is 

0.6 (CV=0) harbor porpoise per year from this stock. 

Table 1. Summary of incidental mortality and serious injury of harbor porpoise (Oregon/Washington Coast stock) 

in commercial and tribal fisheries and calculation of the mean annual mortality rate; n/a indicates that data are not 

available. Mean annual takes are based on 2000-2004 data unless noted otherwise. 

Fishery name Years Data type

Percent 

observer 

coverage

Observed

mortality

Estimated

mortality

Mean annual 

takes (CV in 

parentheses)

Northern WA marine set gillnet 

(tribal fishery in coastal waters: 

areas 4 and 4A)

1999 

2000 

2001 

2002 

2003 

observer

no fishery 

100% 

no fishery 

no fishery 

no fishery 

0 

3 

0 

0 

0 

0 

3 

0 

0 

0 

0.6 (0)1 

Estimated total annual takes 0.6 (0)

1

The 1999-2003 mortality estimates are included in the average. 

 In 1995-1997, data were collected for the coastal portions (areas 4 and 4A) of the northern Washington 

marine set gillnet fishery as part of an experiment, conducted in cooperation with the Makah Tribe, designed to 

explore the merits of using acoustic alarms to reduce bycatch of harbor porpoise in salmon gillnets. Results in 1995-

1996 indicated that the nets equipped with acoustic alarms had significantly lower entanglement rates, as only 2 of 

the 49 mortalities occurred in alarmed nets (Gearin et al. 1996, 2000; Laake et al. 1997b). In 1997, 96% of the sets 

were equipped with acoustic alarms and 13 mortalities were observed (Gearin et al. 2000; P. Gearin, unpubl. data). 

Harbor porpoise were displaced by an acoustic buffer around the alarmed nets, but it is unclear whether the porpoise 

or their prey were repelled by the alarms (Kraus et al. 1997, Laake et al. 1998b). However, the acoustic alarms did 

not appear to affect the target catch (chinook salmon and sturgeon) in the fishery (Gearin et al. 2000). In 2000, 84% 

of the sets (42 of 50 net days) in coastal waters were equipped with acoustic alarms and all three of the observed 

mortalities occurred in nets without alarms. 

 The Marine Mammal Authorization Program (MMAP) fisher self-reports, required of commercial vessel 

operators by the MMPA, are an additional source of information on the number of harbor porpoise killed or 

seriously injured incidental to commercial fishery operations. Between 2000 and 2004, there were no fisher selfreports of harbor porpoise mortalities from any MMAP-listed fishery operating within the range of the 

Oregon/Washington Coast stock. Although these reports are considered incomplete (see details in Appendix 1), 

they represent a minimum mortality. 

 According to Northwest Marine Mammal Stranding Network records, maintained by the NMFS Northwest 

Region, there have been no fishery-related strandings of harbor porpoise from this stock dating back to at least 1990. 

This estimate is considered a minimum because not all stranded animals are found, reported, or examined for cause 

of death (via necropsy by trained personnel). 

Other Mortality

 According to the Marine Mammal Stranding Network records, maintained by the NMFS Northwest 

Region, no human-caused harbor porpoise mortalities or serious injuries were reported from non-fisheries sources in 

2000-2004. This estimate is considered a minimum because not all stranded animals are found, reported, or 

examined for cause of death (via necropsy by trained personnel). 

72
STATUS OF STOCK

 Harbor porpoise are not listed as “depleted” under the MMPA or listed as “threatened” or “endangered” 

under the Endangered Species Act. Based on the currently available data, the level of human-caused mortality and 

serious injury (0.6) does not exceed the PBR (277). Therefore, the Oregon/Washington Coast stock of harbor 

porpoise is not classified as “strategic.” The total fishery mortality and serious injury for this stock (0.6: based on 

observer data) is not known to exceed 10% of the calculated PBR (27.7) and, therefore, can be considered to be 

insignificant and approaching zero mortality and serious injury rate. The status of this stock relative to its Optimum 

Sustainable Population (OSP) level and population trends is unknown. 

REFERENCES

Barlow, J. 1988. Harbor porpoise, Phocoena phocoena, abundance estimation for California, Oregon, and 

Washington: I. Ship surveys. Fish. Bull. 86:417-432. 

Barlow, J., and D. Hanan. 1995. An assessment of the status of harbor porpoise in central California. Rep. Int. 

Whal. Commn. Special Issue 16:123-140. 

Barlow, J., C. W. Oliver, T. D. Jackson, and B. L. Taylor. 1988. Harbor porpoise, Phocoena phocoena, abundance 

estimation for California, Oregon, and Washington: II. Aerial surveys. Fish. Bull. 86:433-444. 

Calambokidis, J., and J. Barlow. 1991. Chlorinated hydrocarbon concentrations and their use for describing 

population discreteness in harbor porpoises from Washington, Oregon, and California. Pp. 101-110, In:

Reynolds, J. E., III, and D. K. Odell (eds.), Proceedings of the second marine mammal stranding workshop: 

3-5 December 1987, Miami, Florida. U.S. Dep. Commer., NOAA Tech. Rep. NMFS 98. 

Calambokidis, J., J. C. Cubbage, J. R. Evenson, S. D. Osmek, J. L. Laake, P. J. Gearin, B. J. Turnock, S. J. Jeffries, 

and R. F. Brown. 1993. Abundance estimates of harbor porpoise in Washington and Oregon waters. Final 

Report by Cascadia Research, Olympia, WA, to National Marine Mammal Laboratory, AFSC, NMFS, 

Seattle, WA. 55 pp. 

Carretta, J. V., J. Barlow, K. A. Forney, M. M. Muto, and J. Baker. 2001. U.S. Pacific marine mammal stock 

assessments: 2001. U.S. Dep. Commer., NOAA Tech. Memo. NMFS-SWFSC-317. 280 pp. 

Chivers, S. J., A. E. Dizon, P. J. Gearin, and K. M. Robertson. 2002. Small-scale population structure of eastern 

North Pacific harbour porpoises (Phocoena phocoena) indicated by molecular genetic analyses. J. 

Cetacean Res. Manage. 4(2):111-122. 

Dohl, T. P., R. C. Guess, M. L. Duman, and R. C. Helm. 1983. Cetaceans of central and northern California, 1980-

1983: status, abundance, and distribution. OCS Study MMS 84-0045. Pacific OCS Region Minerals 

Management Service, 1340 Sixth Street, Los Angeles, CA 90014. 284 pp. 

Gaskin, D. E. 1984. The harbour porpoise Phocoena phocoena (L.): regional populations, status, and information 

on direct and indirect catches. Rep. Int. Whal. Commn. 34:569-586. 

Gearin, P. J. National Marine Mammal Laboratory, AFSC, NMFS, 7600 Sand Point Way NE, Seattle, WA 98115. 

Gearin, P. J., S. R. Melin, R. L. DeLong, H. Kajimura, and M. A. Johnson. 1994. Harbor porpoise interactions with 

a chinook salmon set-net fishery in Washington State. Rep. Int. Whal. Commn. Special Issue 15:427-438. 

Gearin, P. J., M. E. Gosho, L. Cooke, R. DeLong, and J. Laake. 1996. Acoustic alarm experiment in the 1995 

northern Washington marine setnet fishery: methods to reduce by-catch of harbor porpoise. Paper 

SC/48/SM10 presented to the International Whaling Commission, June 1996 (unpublished). 15 pp. 

Available at National Marine Mammal Laboratory, 7600 Sand Point Way NE, Seattle, WA 98115. 

Gearin, P. J., M. E. Gosho, J. L. Laake, L. Cooke, R. L. DeLong, and K. M. Hughes. 2000. Experimental testing of 

acoustic alarms (pingers) to reduce bycatch of harbour porpoise, Phocoena phocoena, in the state of 

Washington. J. Cetacean Res. Manage. 2(1):1-9. 

Green, G. A., J. J. Brueggeman, R. A. Grotefendt, C. E. Bowlby, M. L. Bonnel, and K. C. Balcomb, III. 1992. 

Cetacean distribution and abundance off Oregon and Washington, 1989-1990. Ch. 1, In: Brueggeman, J. J. 

(ed.), Oregon and Washington marine mammal and seabird surveys. Final Report, OCS Study MMS 91-

0093, Minerals Management Service, U.S. Dept. of Interior, Los Angeles, CA. 

Kraus, S. D., A. J. Read, A. Solow, K. Baldwin, T. Spradlin, E. Anderson, and J. Williamson. 1997. Acoustic 

alarms reduce porpoise mortality. Nature 388:525. 

Laake, J. L. National Marine Mammal Laboratory, AFSC, NMFS, 7600 Sand Point Way NE, Seattle, WA 98115. 

Laake, J. L., J. Calambokidis, S. D. Osmek, and D. J. Rugh. 1997a. Probability of detecting harbor porpoise from 

aerial surveys: estimating g(0). J. Wildl. Manage. 61(1):63-75. 

Laake, J. L., P. J. Gearin, M. E. Gosho, and R. L. DeLong. 1997b. Evaluation of effectiveness of pingers to reduce 

incidental entanglement of harbor porpoise in a set gillnet fishery. Pp. 75-81, In: Hill, P. S., and D. P. 

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DeMaster (eds.), MMPA and ESA implementation program, 1996. AFSC Processed Report 97-10. 255 

pp. Available at National Marine Mammal Laboratory, 7600 Sand Point Way NE, Seattle, WA 98115. 

Laake, J., J. Calambokidis, and S. Osmek. 1998a. Survey report for the 1997 aerial surveys for harbor porpoise and 

other marine mammals of Oregon, Washington and British Columbia outside waters. Pp. 77-97, In: Hill, P. 

S., and D. P. DeMaster (eds.), MMPA and ESA implementation program, 1997. AFSC Processed Report 

98-10. 246 pp. Available at National Marine Mammal Laboratory, 7600 Sand Point Way NE, Seattle, WA 

98115. 

Laake, J. L., D. J. Rugh, and L. S. Baraff. 1998b. Observations of harbor porpoise in the vicinity of acoustic alarms 

on a set gillnet. U.S. Dep. Commer., NOAA Tech. Memo. NMFS-AFSC-84. 40 pp. 

Osborne, R., J. Calambokidis, and E. M. Dorsey. 1988. A Guide to Marine Mammals of Greater Puget Sound. 

Island Publishers, Anacortes, WA. 191 pp. 

Osmek, S., P. Rosel, A. Dizon, and R. DeLong. 1994. Harbor porpoise, Phocoena phocoena, population 

assessment in Oregon and Washington, 1993. Pp. 1-14, In: Braham, H. W., and D. P. DeMaster (eds.), 

Marine mammal assessment program: status of stocks and impacts of incidental take, 1993. National 

Marine Mammal Laboratory – MMPA Studies of 1993, NMML, AFSC, NMFS, NOAA. 153 pp. 

Available at National Marine Mammal Laboratory, 7600 Sand Point Way NE, Seattle, WA 98115. 

Osmek, S., J. Calambokidis, J. Laake, P. Gearin, R. DeLong, J. Scordino, S. Jeffries, and R. Brown. 1996. 

Assessment of the status of harbor porpoise, Phocoena phocoena, in Oregon and Washington waters. U.S. 

Dep. Commer., NOAA Tech. Memo. NMFS-AFSC-76. 46 pp. 

Rosel, P. E. 1992. Genetic population structure and systematic relationships of some small cetaceans inferred from 

mitochondrial DNA sequence variation. Ph.D. Thesis, University of California - San Diego, La Jolla, CA. 

191 pp. 

Rosel, P. E., A. E. Dizon, and M. G. Haygood. 1995. Variability of the mitochondrial control region in populations 

of the harbour porpoise, Phocoena phocoena, on inter-oceanic and regional scales. Can. J. Fish. and Aquat. 

Sci. 52:1210-1219. 

Wade, P. R., and R. Angliss. 1997. Guidelines for assessing marine mammal stocks: report of the GAMMS 

workshop April 3-5, 1996, Seattle, Washington. U.S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

74
Revised 12/15/2006

HARBOR PORPOISE (Phocoena phocoena): 

Washington Inland Waters Stock

STOCK DEFINITION AND GEOGRAPHIC RANGE

In the eastern North Pacific Ocean, harbor 

porpoise are found in coastal and inland waters from

Point Barrow, along the Alaskan coast, and down the 

west coast of North America to Point Conception,

California (Gaskin 1984). Harbor porpoise are known to

occur year-round in the inland trans-boundary waters of

Washington and British Columbia, Canada (Osborne et 

al. 1988), and along the Oregon/Washington coast 

(Barlow 1988, Barlow et al. 1988, Green et al. 1992).

Aerial survey data from coastal Oregon and Washington, 

collected during all seasons, suggest that harbor porpoise 

distribution varies by depth (Green et al. 1992). 

Although distinct seasonal changes in abundance along 

the west coast have been noted, and attributed to possible 

shifts in distribution to deeper offshore waters during late 

winter (Dohl et al. 1983, Barlow 1988), seasonal

movement patterns are not fully understood.

Investigation of pollutant loads in harbor

porpoise ranging from California to the Canadian border

suggests restricted harbor porpoise movements 

(Calambokidis and Barlow 1991). Stock discreteness in

the eastern North Pacific was analyzed using 

mitochondrial DNA from samples collected along the 

west coast (Rosel 1992) and is summarized in Osmek et 

al. (1994). Two distinct mtDNA groupings or clades

exist. One clade is present in California, Washington, 

British Columbia, and Alaska (no samples were available 

from Oregon), while the other is found only in California 

and Washington. Although these two clades are not

geographically distinct by latitude, the results may

indicate a low mixing rate for harbor porpoise along the

west coast of North America. Further genetic testing of

the same data, along with additional samples, found significant genetic differences for four of the six pair-wise 

comparisons between the four areas investigated: California, Washington, British Columbia, and Alaska (Rosel et 

al. 1995). These results demonstrate that harbor porpoise along the west coast of North America are not panmictic

or migratory and that movement is sufficiently restricted that genetic differences have evolved. Recent preliminary 

genetic analyses of samples ranging from Monterey Bay, California, to Vancouver Island, British Columbia, 

indicate that there is small-scale subdivision within the U.S. portion of this range (Chivers et al. 2002). This is

consistent with low movement suggested by genetic analysis of harbor porpoise specimens from the North Atlantic, 

where numerous stocks have been delineated with clinal differences over areas as small as the waters surrounding 

the British Isles. 

Oregon/

Washington

Coast stock

Washington

Inland Waters

stock

Oregon

Washington

Cape Blanco

126°W

126°W

124°W 122°W 120°W

42°N

44°N

46°N

48°N

Figure 1. Stock boundaries (dashed lines) and

approximate distribution (shaded areas) of harbor

porpoise along the coasts of Washington and northern

Oregon.

Using the 1990-1991 aerial survey data of Calambokidis et al. (1993) for water depths <50 fathoms, Osmek

et al. (1996) found significant differences in harbor porpoise mean densities (z=5.9, p<0.01) between the waters of

coastal Oregon/Washington and inland Washington/southern British Columbia, Canada (i.e., Strait of Juan de

Fuca/San Juan Islands). Although differences in density exist between coastal Oregon/Washington and inland

Washington waters, a specific stock boundary line cannot be identified based upon biological or genetic differences.

However, harbor porpoise movements and rates of intermixing within the eastern North Pacific are restricted, and 

there has been a significant decline in harbor porpoise sightings within southern Puget Sound since the 1940s;

therefore, following a risk averse management strategy, two stocks are recognized: the Oregon/Washington Coast

stock (between Cape Blanco, OR, and Cape Flattery, WA) and the Washington Inland Waters stock (in waters east

75
of Cape Flattery) (see Fig. 1). Recent genetic evidence suggests that the population of eastern North Pacific harbor 

porpoise is more finely structured than is currently recognized (Chivers et al. 2002). All relevant data (e.g., genetic 

samples, contaminant studies, and satellite tagging) will be reviewed to determine whether to adjust the stock 

boundaries for harbor porpoise in Oregon and Washington waters. 

 In their assessment of California harbor porpoise, Barlow and Hanan (1995) recommended two stocks be 

recognized in California, with the stock boundary at the Russian River. Based on recent genetic findings (Chivers et 

al. 2002), California coast stocks were re-evaluated and significant genetic differences were found among four 

identified sampling sites. Revised stock boundaries, based on these genetic data and density discontinuities 

identified from aerial surveys, resulted in six California/Oregon/Washington stocks where previously there had been 

four (Carretta et al. 2001): 1) the Washington Inland Waters stock, 2) the Oregon/Washington Coast stock, 3) the 

Northern California/Southern Oregon stock, 4) the San Francisco-Russian River stock, 5) the Monterey Bay stock, 

and 6) the Morro Bay stock. The stock boundaries for animals that occur in Washington/northern Oregon waters are 

shown in Figure 1. This report considers only the Washington Inland Waters stock. Stock assessment reports for 

Oregon/Washington Coast, Northern California/Southern Oregon, San Francisco-Russian River, Monterey Bay, and 

Morro Bay harbor porpoise also appear in this volume. Stock assessment reports for the three harbor porpoise 

stocks in the inland and coastal waters of Alaska, including 1) the Southeast Alaska stock, 2) the Gulf of Alaska 

stock, and 3) the Bering Sea stock, are reported separately in the Stock Assessment Reports for the Alaska Region. 

The harbor porpoise occurring in British Columbia have not been included in any of the U.S. stock assessment 

reports. 

POPULATION SIZE

 Aerial surveys of the inside waters of Washington and southern British Columbia were conducted during 

August of 2002 and 2003 (J. Laake, unpubl. data). These aerial surveys included the Strait of Juan de Fuca, San 

Juan Islands, Gulf Islands, and Strait of Georgia, which includes waters inhabited by the Washington Inland Waters 

stock of harbor porpoise as well as harbor porpoise from British Columbia. An average of the 2002 and 2003 

estimates of abundance in U.S. waters results in an uncorrected abundance of 3,123 (CV= 0.10) harbor porpoise in 

Washington inland waters (J. Laake, unpubl. data). When corrected for availability and perception bias, using a 

correction factor of 3.42 (1/g(0); g(0)=0.292, CV=0.366) (Laake et al. 1997), the estimated abundance for the 

Washington Inland Waters stock of harbor porpoise is 10,682 (CV=0.38) animals (J. Laake, unpubl. data). 

Minimum Population Estimate

 The minimum population estimate for this stock is calculated as the lower 20th percentile of the log-normal 

distribution (Wade and Angliss 1997) of the average of the 2002 and 2003 population estimates (10,682), which is 

7,841 harbor porpoise. 

Current Population Trend 

 There are no reliable data on long-term population trends of harbor porpoise for most waters of Oregon, 

Washington, or British Columbia, however, the uncorrected estimate of abundance in Washington inland waters was 

significantly greater in 2002/2003 than in 1996 (3,123 vs. 1,025; Z=6.16, P<0.0001) (Calambokidis et al. 1997; J. 

Laake, unpubl. data). 

 A different situation exists in southern Puget Sound where harbor porpoise are rarely observed, in contrast 

to 1942 when they were common in those waters (Scheffer and Slipp 1948). Although quantitative data for this area 

are lacking, marine mammal survey effort (Everitt et al. 1980), stranding records since the early 1970s (Osmek et al. 

1995), and the results of harbor porpoise surveys of 1991 (Calambokidis et al. 1992) and 1994 (Osmek et al. 1995) 

indicate that harbor porpoise abundance has declined in southern Puget Sound. In 1994, a total of 769 km of vessel 

survey effort and 492 km of aerial survey effort conducted during favorable sighting conditions produced no 

sightings of harbor porpoise in southern Puget Sound. Reasons for the apparent decline are unknown, but it may be 

related to fishery interactions, pollutants, vessel traffic, or other factors (Osmek et al. 1995). Recently, however, 

there have been confirmed sightings of harbor porpoise in central Puget Sound (R. DeLong, pers. comm.). 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 A reliable estimate of the maximum net productivity rate is not currently available for harbor porpoise. 

Hence, until additional data become available, it is recommended that the cetacean maximum theoretical net 

productivity rate (RMAX) of 4% (Wade and Angliss 1997) be employed for the Washington Inland Waters harbor 

porpoise stock. 

76
POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size 

(7,841) times one-half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.40 

(for a stock of unknown status with a mortality rate CV≥0.80, Wade and Angliss 1997), resulting in a PBR of 63 

harbor porpoise per year.

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fisheries Information

 Fishing effort in the northern Washington marine set gillnet fishery (areas 4, 4A, 4B, and 5) is conducted 

within the range of both harbor porpoise stocks (Oregon/Washington Coast and Washington Inland Waters) 

occurring in Washington State waters. Some movement of harbor porpoise between Washington’s coastal and 

inland waters is likely, but it is currently not possible to quantify the extent of such movements. For the purposes of 

this stock assessment report, the animals taken in waters east of Cape Flattery (areas 4B and 5) are assumed to have 

belonged to the Washington Inland Waters stock, and Table 1 includes data only from that portion of the fishery. 

NMFS observers monitored 58% of the 36 net days (1 net day equals a 100-fathom length net set for 24 hours) of 

fishing effort in inland waters in 2000. There was no observer program in 1999 or 2001-2003 in inland waters; 

fishing effort was 4, 46, 4.5, and 7 net days (respectively) in those years, and no harbor porpoise takes were reported 

(Gearin et al. 1994; 2000; P. Gearin, unpubl. data). No mortalities were reported in the inland portion of the fishery 

between 1999 and 2003, thus, the mean estimated mortality for this fishery is zero harbor porpoise per year from this 

stock. 

 In 1993, as a pilot for future observer programs, NMFS in conjunction with the Washington Department of 

Fish and Wildlife (WDFW) monitored non-treaty components (areas 7, 7A, 7B/7C, 8A/8D, 10/11, and 12/12A/12B) 

of the Washington Puget Sound Region salmon gillnet fishery (Pierce et al. 1994). Observer coverage was 1.5% 

overall, ranging from 0.9% to 7.3% for the various components of the fishery. No harbor porpoise mortalities were 

reported (Table 1). Pierce et al. (1994) cautioned against extrapolating these mortalities to the entire Puget Sound 

fishery due to the low observer coverage and potential biases inherent in the data. The area 7/7A sockeye landings 

represented the majority of the non-treaty salmon landings in 1993, approximately 67%. Results of this pilot study 

were used to design the 1994 observer programs discussed below. 

 In 1994, NMFS in conjunction with WDFW conducted an observer program during the Puget Sound nontreaty chum salmon gillnet fishery (areas 10/11 and 12/12B). A total of 230 sets were observed during 54 boat trips, 

representing approximately 11% observer coverage of the 500 fishing boat trips comprising the total effort in this 

fishery, as estimated from fish ticket landings (Erstad et al. 1996). No harbor porpoise were reported within 100 m 

of observed gillnets. The Puget Sound treaty chum salmon gillnet fishery in Hood Canal (areas 12, 12B, and 12C) 

and Puget Sound treaty sockeye/chum gillnet fishery in the Strait of Juan de Fuca (areas 4B, 5, and 6C) were also 

monitored in 1994 (NWIFC 1995). No harbor porpoise mortalities were reported in the observer programs covering 

these treaty salmon gillnet fisheries, where observer coverage was estimated at 2.2% (based on % of total catch 

observed) and approximately 7.5% (based on % of observed trips to total landings), respectively. 

 Also in 1994, NMFS in conjunction with WDFW and the Tribes conducted an observer program to 

examine seabird and marine mammal interactions with the Puget Sound treaty and non-treaty sockeye salmon gillnet 

fishery (areas 7 and 7A). During this fishery, observers monitored 2,205 sets, representing approximately 7% of the 

estimated 33,086 sets occurring in the fishery (Pierce et al. 1996). There was one observed harbor porpoise 

mortality (one other was entangled and released alive with no indication that it was injured), resulting in a mortality 

rate of 0.00045 harbor porpoise per set, which extrapolates to 15 mortalities (CV=1.0) for the entire fishery. 

 In 1996, Washington Sea Grant Program conducted a test fishery in the non-treaty sockeye salmon gillnet 

fishery (area 7) to compare entanglement rates of seabirds and marine mammals and catch rates of salmon using 

three experimental gears and a control (monofilament mesh net). The experimental nets incorporated highly visible 

mesh in the upper quarter (50 mesh gear) or upper eighth (20 mesh gear) of the net or had low-frequency sound 

emitters attached to the corkline (Melvin et al. 1997). In 642 sets during 17 vessel trips, 2 harbor porpoise were 

killed in the 50 mesh gear. 

77
Table 1. Summary of incidental mortality and serious injury of harbor porpoise (Washington Inland Waters stock) 

due to commercial and tribal fisheries and calculation of the mean annual mortality rate; n/a indicates that data are 

not available. Mean annual takes are based on 2000-2004 data unless noted otherwise. 

Fishery name Years

Data 

type

Percent 

observer 

coverage

Observed

mortality

Estimated

mortality

Mean annual 

takes (CV in 

parentheses)

Northern WA marine set gillnet 

(tribal fishery in inland waters: 

areas 4B and 5)

1999 

2000 

2001 

2002 

2003 

observer

0% 

58% 

0% 

0% 

0% 

n/a 

0 

n/a 

n/a 

n/a 

n/a 

0 

n/a 

n/a 

n/a 

01

WA Puget Sound Region salmon 

set/drift gillnet (observer programs 

listed below covered segments of 

this fishery):

- - - - - -

Puget Sound non-treaty salmon 

gillnet (all areas and species) 1993 observer 1.3% 0 0 see text

Puget Sound non-treaty chum 

salmon gillnet (areas 10/11 and 

12/12B)

1994 observer 11% 0 0 0

Puget Sound treaty chum 

salmon gillnet (areas 12, 12B, 

and 12C)

1994 observer 2.2% 0 0 0

Puget Sound treaty chum and 

sockeye salmon gillnet (areas 

4B, 5, and 6C)

1994 observer 7.5% 0 0 0

Puget Sound treaty and nontreaty sockeye salmon gillnet 

(areas 7 and 7A)

1994 observer 7% 1 15 15 (1.0)

Unknown Puget Sound fishery 2000-2004 stranding 1, 0, 0, 0, 0 ≥0.2 (n/a)

Minimum total annual takes ≥15.2 (1.0)

1

Only the 2000 mortality estimate is included in the average.

 Combining the estimates from the 1994 observer programs (15) with the northern Washington marine set 

gillnet fishery (zero) results in an estimated mean mortality rate in observed fisheries of 15 harbor porpoise per year 

from this stock. It should be noted that the 1994 observer programs did not sample all segments of the entire 

Washington Puget Sound Region salmon set/drift gillnet fishery and, further, the extrapolation of total kill did not 

include effort for the unobserved segments of this fishery. Therefore, 15 is an underestimate of the harbor porpoise 

mortality due to the entire fishery. Although the percentage of the overall Washington Puget Sound Region salmon 

set/drift gillnet fishery effort that was observed in 1994 was not quantified, the observer programs covered those 

segments of the fishery which had the highest salmon catches, the majority of vessel participation, and the highest 

likelihood of interaction with harbor porpoise (J. Scordino, pers. comm.). Since the Washington Inland Waters 

stock of harbor porpoise occurs primarily in the Strait of Juan de Fuca and the San Juan Islands, it is unlikely that 

many harbor porpoise are taken in other areas of the Washington Puget Sound Region salmon gillnet fishery (i.e., 

Hood Canal and southern Puget Sound). Harbor porpoise takes in the Washington Puget Sound Region salmon drift 

gillnet fishery are unlikely to have increased since the fishery was last observed in 1994, due to reductions in the 

number of participating vessels and available fishing time (see details in Appendix 1). Fishing effort and catch have 

declined throughout all salmon fisheries in the region due to management efforts to recover ESA-listed salmonids. 

 The Marine Mammal Authorization Program (MMAP) fisher self-reports, required of commercial vessel 

operators by the MMPA, are an additional source of information on the number of harbor porpoise killed or 

seriously injured incidental to commercial fishery operations. Between 2000 and 2004, there were no fisher selfreports of harbor porpoise mortalities from any MMAP-listed Washington Puget Sound Region salmon set/drift 

gillnet fishery. Unlike the 1994 observer program data, the self-reported fisheries data cover the entire fishery. 

Although these reports are considered incomplete (see details in Appendix 1), they represent a minimum mortality. 

78
 Strandings of harbor porpoise wrapped in fishing gear or with serious injuries caused by interactions with 

gear are a final source of fishery-related mortality information. According to Northwest Marine Mammal Stranding 

Network records, maintained by the NMFS Northwest Region, one fishery-related stranding of a harbor porpoise 

occurred in 2000 in Bellingham Harbor. As the stranding could not be attributed to a particular fishery, it has been 

included in Table 1 as occurring in an unknown Puget Sound fishery. Fishery-related strandings during 2000-2004 

resulted in an estimated annual mortality of 0.2 harbor porpoise from this stock. This estimate is considered a 

minimum because not all stranded animals are found, reported, or examined for cause of death (via necropsy by 

trained personnel). 

 Although, commercial gillnet fisheries in Canadian waters are known to have taken harbor porpoise in the 

past (Barlow et al. 1994, Stacey et al. 1997), few data are available because the fisheries were not monitored. In 

2001, the Department of Fisheries and Oceans, Canada, conducted a federal fisheries observer program and a survey 

of license holders to estimate the incidental mortality of harbor porpoise in selected salmon fisheries in southern 

British Columbia (Hall et al. 2002). Based on the observed bycatch of porpoise (2 harbor porpoise mortalities) in 

the 2001 fishing season, the estimated mortality for southern British Columbia in 2001 was 20 porpoise per 810 boat 

days fished or a total of 80 harbor porpoise. However, it is not known how many harbor porpoise from the 

Washington Inland Waters stock are currently taken in the waters of southern British Columbia. 

 The minimum estimated fishery mortality and serious injury for this stock is 15.2 harbor porpoise per year, 

based on observer program data (15) and stranding data (0.2) in U.S. waters. 

Other Mortality

 According to Northwest Marine Mammal Stranding Network records, maintained by the NMFS Northwest 

Region, one human-caused harbor porpoise mortality was reported from non-fisheries sources in 2000-2004. An 

animal was struck by a ship in 2001, resulting in an estimated mortality of 0.2 harbor porpoise per year from this 

stock. 

STATUS OF STOCK

 Harbor porpoise are not listed as “depleted” under the MMPA or listed as “threatened” or “endangered” 

under the Endangered Species Act. Based on currently available data, the total level of human-caused mortality and 

serious injury (15.2 + 0.2 = 15.4) is not known to exceed the PBR (63). Therefore, the Washington Inland Waters 

harbor porpoise stock is not classified as “strategic.” The minimum total fishery mortality and serious injury for this 

stock (15.2) exceeds 10% of the calculated PBR (6.3) and, therefore, cannot be considered to be insignificant and 

approaching zero mortality and serious injury rate. The status of this stock relative to its Optimum Sustainable 

Population (OSP) level and population trends is unknown, although harbor porpoise sightings in southern Puget 

Sound have declined since the 1940s. 

 This stock is not recognized as “strategic,” however, the mortality rate is based on observer data from a 

subset of the Washington Puget Sound Region salmon set/drift gillnet fishery that was last observed in 1994. 

Evaluation of the estimated take level is complicated by a lack of knowledge about the extent to which harbor 

porpoise from U.S. waters frequent the waters of British Columbia and are, therefore, subject to fishery-related 

mortality. Given that the estimated take level is from 1994, it is appropriate to consider whether the current take 

level is different. No new information is available about mortality per set, but 1) fishing effort has decreased in 

recent years and 2) analysis of data from aerial surveys in 2002 and 2003 indicates that abundance has increased 

since 1996. 

REFERENCES

Barlow, J. 1988. Harbor porpoise, Phocoena phocoena, abundance estimation for California, Oregon, and 

Washington: I. Ship surveys. Fish. Bull. 86:417-432. 

Barlow, J., and D. Hanan. 1995. An assessment of the status of harbor porpoise in central California. Rep. Int. 

Whal. Commn. Special Issue 16:123-140. 

Barlow, J., C. W. Oliver, T. D. Jackson, and B. L. Taylor. 1988. Harbor porpoise, Phocoena phocoena, abundance 

estimation for California, Oregon, and Washington: II. Aerial surveys. Fish. Bull. 86:433-444. 

Barlow, J., R. W. Baird, J. E. Heyning, K. Wynne, A. M. Manville, II, L. F. Lowry, D. Hanan, J. Sease, and V. N. 

Burkanov. 1994. A review of cetacean and pinniped mortality in coastal fisheries along the west coast of 

the USA and Canada and the east coast of the Russian Federation. Rep. Int. Whal. Commn. Special Issue 

15:405-425. 

Calambokidis, J., and J. Barlow. 1991. Chlorinated hydrocarbon concentrations and their use for describing 

population discreteness in harbor porpoises from Washington, Oregon, and California. Pp. 101-110, In:

79
Reynolds, J. E., III, and D. K. Odell (eds.), Proceedings of the second marine mammal stranding workshop: 

3-5 December 1987, Miami, Florida. U.S. Dep. Commer., NOAA Tech. Rep. NMFS 98. 

Calambokidis, J., J. R. Evenson, J. C. Cubbage, P. J. Gearin, and S. D. Osmek. 1992. Harbor porpoise distribution 

and abundance off Oregon and Washington from aerial surveys in 1991. Final Report by Cascadia 

Research, Olympia, WA, to National Marine Mammal Laboratory, AFSC, NMFS, Seattle, WA. 44 pp. 

Calambokidis, J., J. C. Cubbage, J. R. Evenson, S. D. Osmek, J. L. Laake, P. J. Gearin, B. J. Turnock, S. J. Jeffries, 

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Seattle, WA. 55 pp. 

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British Columbia inside waters. Final Report by Cascadia Research, Olympia, WA, to National Marine 

Mammal Laboratory, AFSC, NMFS, Seattle, WA. 96 pp. 

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assessments: 2001. U.S. Dep. Commer., NOAA Tech. Memo. NMFS-SWFSC-317. 280 pp. 

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98115. 

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management areas 10/11 & 12/12B: nontreaty chum gill net fishery. Final Report, Washington Dept. Fish 

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134 pp. 

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acoustic alarms (pingers) to reduce bycatch of harbour porpoise, Phocoena phocoena, in the state of 

Washington. J. Cetacean Res. Manage. 2(1):1-9. 

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Salmon Fisheries Science Program, Fisheries and Oceans Canada. 51 pp. 

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aerial surveys: estimating g(0). J. Wildl. Manage. 61(1):63-75. 

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gillnet salmon fisheries. 1996 Sockeye and 1995 Chum Salmon Test Fisheries Final Report, Washington 

Sea Grant Program, Seattle, WA. 48 pp. 

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Unpubl. Report. 41 pp. Available at NWIFC, 6730 Martin Way E, Olympia, WA 98516. 

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Island Publishers, Anacortes, WA. 191 pp. 

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81
Revised 10/30/2007

DALL'S PORPOISE (Phocoenoides dalli): 

California/Oregon/Washington Stock

STOCK DEFINITION AND 

GEOGRAPHIC RANGE

 Dall's porpoise are endemic 

to temperate waters of the North 

Pacific Ocean. Off the U.S. west 

coast, they are commonly seen in 

shelf, slope and offshore waters 

(Figure 1; Morejohn 1979). 

Sighting patterns from aerial and 

shipboard surveys conducted in 

California, Oregon and Washington 

at different times (Green et al. 1992, 

1993; Mangels and Gerrodette 

1994; Barlow 1995; Forney et al. 

1995) suggest that north-south 

movement between these states 

occurs as oceanographic conditions 

change, both on seasonal and interannual time scales. The southern 

end of this population's range is not 

well-documented, but they are 

commonly seen off Southern 

California in winter, and during 

cold-water periods they probably 

range into Mexican waters off 

northern Baja California. The stock 

structure of eastern North Pacific 

Dall's porpoise is not known, but 

based on patterns of stock 

differentiation in the western North 

Pacific, where they have been more 

intensively studied, it is expected that 

separate stocks will emerge when 

data become available (Perrin and 

Brownell 1994). Although Dall's 

porpoise are not restricted to U.S. 

territorial waters, there are no 

cooperative management agreements 

with Mexico or Canada for fisheries 

which may take this species (e.g. 

gillnet fisheries). For the Marine Mammal Protection Act (MMPA) stock assessment reports, Dall's 

porpoises within the Pacific U.S. Exclusive Economic Zone are divided into two discrete, non-contiguous 

areas: 1) waters off California, Oregon and Washington (this report), and 2) Alaskan waters. 

OREGON

WASHINGTON

CALIFORNIA

POPULATION SIZE

eys are expected to be more reliable for this species than aerial surveys because of 

e larg

 Shipboard surv

th e, unknown fraction of diving animals missed from the air (Forney 1994). Two summer/fall 

shipboard surveys were conducted within 300 nmi of the coasts of California Oregon and Washington in 

2001 (Barlow 2003) and 2005 (Forney 2007). The distribution of Dall’s porpoise throughout this region is 

Figure 1. Dall’s porpoise sightings based on aerial and 

shipboard surveys off California, Oregon, and 

Washington, 1991-2005 (see Appendix 2 for data 

sources and information on timing and location of 

survey effort). Dashed line represents the U.S. EEZ, 

thin lines represent completed transect effort of all 

surveys combined. Key: ● = summer/autumn shipbased sightings; ■ = winter/spring aerial-based sightings. 

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

45°0'0"N

40°0'0"N

82
highly variable between years and appears to be affected by oceanographic conditions (Forney 1997; 

Forney and Barlow 1998). Because animals may spend time outside the U.S. Exclusive Economic Zone as 

oceanographic conditions change, a multi-year average abundance estimate is the most appropriate for 

management within U.S. waters. The geometric mean abundance estimate for California, Oregon and 

Washington waters based on 2001 and 2005 ship surveys is 57,549 (CV = 0.34) Dall’s porpoise (Barlow 

2003; Forney 2007). Additional numbers of Dall’s porpoise occur in the inland waters of Washington 

state, but the most recent abundance estimate obtained in 1996 (900 animals, CV = 0.40) is over 8 years old 

(Calambokidis et al. 1997) and is not included in the overall estimate of abundance for this stock. 

Minimum Population Estimate

tile of the 2001-2005 average abundance estimate for the outer coast 

f Califo

urrent Population Trend

ailable regarding trends in abundance of Dall's porpoise in California, Oregon 

nd Was

URRENT AND MAXIMUM NET PRODUCTIVITY RATES

tes is available for Dall's porpoise off 

OTENTIAL BIOLOGICAL REMOVAL

BR) level for this stock is calculated as the minimum 

lati

 The log-normal 20th percen

o rnia, Oregon and Washington waters is 43,425 Dall's porpoise. 

C

 No information is av

a hington. Their distribution and abundance in this region varies considerably at both seasonal and 

interannual time scales as oceanographic conditions vary (Forney 1997; Forney and Barlow 1998). 

C

 No information on current or maximum net productivity ra

the U.S. west coast. 

P

 The potential biological removal (P

popu on size (43,425) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times

a recovery factor of 0.40 (for a species of unknown status and mortality rate CV; Wade and Angliss 1997), 

resulting in a PBR of 347 Dall’s porpoise per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

f recent fishery mortality and injury for this stock of Dall’s porpoise is given in 

able 1.

aja 

liforn

’s porpoise have also been documented in the 

liforni

Fishery Information

 A summary o

T More detailed information on these fisheries is provided in Appendix 1. Mortality estimates for 

the California drift gillnet fishery are included for the five most recent years of monitoring, 2000-2004 

(Carretta and Chivers 2004, Carretta et al. 2005a, 2005b). After the 1997 implementation of a Take 

Reduction Plan, which included skipper education workshops and required the use of pingers and minimum 

6-fathom extenders, overall cetacean entanglement rates in the drift gillnet fishery dropped considerably 

(Barlow and Cameron 2003). However, because of interannual variability in entanglement rates and the 

relative rarity of Dall’s porpoise entanglements, additional years of data will be required to fully evaluate 

the effectiveness of pingers for reducing mortality of this particular species. Mean annual takes in Table 1 

are based on 2000-2004 data. This results in an average estimate of 1.2 Dall’s porpoise taken annually. 

 Drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of B

Ca ia, Mexico and may take animals from this population. Quantitative data are available only for the 

Mexican swordfish drift gillnet fishery, which uses vessels, gear, and operational procedures similar to 

those in the U.S. drift gillnet fishery, although nets may be up to 4.5 km long (Holts and Sosa-Nishizaki 

1998). The fleet increased from two vessels in 1986 to 31 vessels in 1993 (Holts and Sosa-Nishizaki 1998). 

The total number of sets in this fishery in 1992 can be estimated from data provided by these authors to be 

approximately 2700, with an observed rate of marine mammal bycatch of 0.13 animals per set (10 marine 

mammals in 77 observed sets; Sosa-Nishizaki et al. 1993). This overall mortality rate is similar to that 

observed in California driftnet fisheries during 1990-95 (0.14 marine mammals per set; Julian and Beeson, 

1998), but species-specific information is not available for the Mexican fisheries. Previous efforts to 

convert the Mexican swordfish driftnet fishery to a longline fishery have resulted in a mixed-fishery, with 

20 vessels alternately using longlines or driftnets, 23 using driftnets only, 22 using longlines only, and 

seven with unknown gear type (Berdegué 2002). 

 Low levels of mortality for Dall

Ca a/Oregon/Washington domestic groundfish trawl fisheries (Perez and Loughlin 1991; Perez 2003). 

Between 2000 and 2004 with 80%-100% of the fishing effort observed, one Dall’s porpoise was reported 

83
killed in the at-sea processing portion of the Pacific whiting trawl fishery. In addition, one Dall’s porpoise 

was reported killed in 2004 under the MMAP self-reporting program. Currently, there are no estimates of 

Dall’s porpoise mortality available from this fishery. 

Table 1. Summary of available information on the incidental mortality and injury of Dall's porpoise 

ther Mortality 

’s porpoise strandings between 2000-2004 showed evidence of a vessel collision as the 

ause of

TATUS OF STOCK

all's porpoise in California, Oregon and Washington relative to OSP is not known, 

nd ther

EFERENCES

 The abundance of cetaceans in California waters. Part I: Ship surveys in summer and fall 

Barlow, tes of cetacean abundance off California, Oregon and Washington 

Fishery Name Data Type Yea (s) 

Percent Observed Estimated Annual Mean Annual 

(California/ Oregon/Washington Stock) in commercial fisheries that might take this species. All observed 

entanglements of Dall's porpoise resulted in the death of the animal. Coefficients of variation for mortality 

estimates are provided in parentheses; n/a = not available. Mean annual takes are based on 2000-2004 data 

unless noted otherwise. MMAP refers to fisher self-reports of incidental takes under the Marine Mammal 

Authorization Program. 

r Observer 

Coverage Mortality Takes (CV in 

parentheses) Mortality 

CA/OR thresher 

sh t obs ver 

2000 

0 (

22.9% 0 0 

O

Two Dall

c death. This results in an average annual mortality of 0.4 Dall’s porpoise caused by vessel 

collisions. 

S

 The status of D

a e are insufficient data to evaluate potential trends in abundance. No habitat issues are known to be 

of concern for this species. They are not listed as "threatened" or "endangered" under the Endangered 

Species Act nor as "depleted" under the MMPA. The average annual human-caused mortality in 2000-

2004 (fishery mortality + vessel collisions = 1.8 animals) is estimated to be less than the PBR (347), and 

therefore they are not classified as a "strategic" stock under the MMPA. The total fishery mortality and 

serious injury for this stock is less than 10% of the calculated PBR and, therefore, can be considered to be 

insignificant and approaching zero mortality and serious injury rate.

R

Barlow, J. 1995. 

of 1991. Fish. Bull. 93:1-14. 

J. 1997. Preliminary estima

based on a 1996 ship survey and comparisons of passing and closing modes. Admin. Rep. LJ-97-

ark/swordfish drif

gillnet fishery 

er

data 

2001 

2002 

20.4% 

22.1% 

0 

0 

0 

0 

2003 20.2% 0 0 n/a) 

2004 20.6% 0 0 

2000 80.6% 0 0 

WA/OR/CA domestic 

Observer data 

MMAP 2004 n/a 

1 0.2 ( /a) 

≥1 (n/a) 

2001 

2002 

2003 

2004 

96.2% 

100% 

100% 

100% 

0 

1 

0 

0 

0 

 (0) 

0 

0 

n

groundfish trawl 

1 1 

Puget Sound salmon drift 

MMAP 2000-2004 n/a 1 1 ≥0.2 (n/a) gillnet (tribal fishery, 

Area 5, Strait of Juan de 

Fuca) 

Minimum total annual takes 1.4 (n/a) 

84
11. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 25p. 

Barlow, J. and T. Gerrodette. 1996. Abundance of cetaceans in California waters based on 1991 and 1993 

ship surveys. U.S. Dep. Commer., NOAA Tech. Memo. NMFS-SWFSC-233. 15 pp. 

Barlow, J. and G. A. Cameron. 2003. Field experiments show that acoustic pingers reduce marine mammal 

bycatch in the California drift gillnet fishery. Marine Mammal Science 19(2):265-283. 

Barlow, J. 2003. Preliminary estimates of the abundance of cetaceans along the U.S. west coast: 

1991_2001. Southwest Fisheries Science Center Administrative Report LJ_03_03. Available 

from SWFSC, 8604 La Jolla Shores Dr., La Jolla CA 92037. 31p. 

Berdegué, J. 2002. Depredación de las especies pelágicas reservadas a la pesca deportiva y especies en 

peligro de extinción con uso indiscriminado de artes de pesca no selectivas (palangres, FAD's, 

trampas para peces y redes de agallar fijas y a la deriva) por la flota palangrera Mexicana. 

Fundación para la conservación de los picudos. A.C. Mazatlán, Sinaloa, 21 de septiembre. 

Calambokidis, J., S. Osmek, and J. L. Laake. 1997. Aerial surveys for marine mammals in Washington 

and British Columbia inside waters. Final Contract Report for Contract 52ABNF-6-00092, 

available from Cascadia Research Collective, Waterstreet Building 218 1⁄2 West Forth Avenue, 

Olympia, Washington 98501. 

Carretta, J.V. and S.J. Chivers. 2004. Preliminary estimates of marine mammal mortality and biological 

sampling of cetaceans in California gillnet fisheries for 2003. Paper SC/56/SM1 presented to the 

IWC Scientific Committee, June 2004 (unpublished). [Available from Southwest Fisheries 

Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 

92037, USA]. 

Carretta, J.V., S.J. Chivers, and K. Danil. 2005a. Preliminary estimates of marine mammal bycatch, 

mortality, and biological sampling of cetaceans in California gillnet fisheries for 2004. 

Administrative Report LJ-05-10, available from Southwest Fisheries Science Center, 8604 La 

Jolla Shores Drive, La Jolla, California, 92037. 17 p. 

Carretta, J.V., T. Price, D. Petersen, and R. Read. 2005b. Estimates of marine mammal, sea turtle, and 

seabird mortality in the California drift gillnet fishery for swordfish and thresher shark, 1996-

2002. Marine Fisheries Review 66(2):21-30. 

Forney, K. A. 1994. Recent information on the status of odontocetes in Californian waters. U.S. Dep. 

Commer., NOAA Tech. Memo. NMFS-SWFSC-202. 87 pp. 

Forney, K. A. 1997. Patterns of variability and environmental models of relative abundance for California 

cetaceans. Ph.D. dissertation, Scripps Institution of Oceanography, University of California, San 

Diego. 

Forney, K. A. and J. Barlow. 1998. Seasonal patterns in the abundance and distribution of California 

cetaceans, 1991-92. Mar. Mamm. Sci. 14:460-489. 

Forney, K. A., J. Barlow and J. V. Carretta. 1995. The abundance of cetaceans in California waters. Part 

II: Aerial surveys in winter and spring of 1991 and 1992. Fish. Bull. 93:15-26. 

Forney, K.A. 2007. Preliminary estimates of cetacean abundance along the U.S. west coast and within 

four National Marine Sanctuaries during 2005. U.S. Department of Commerce, NOAA Technical 

Memorandum NMFS-SWFSC-406. 27 p. 

Green, G., J. J. Brueggeman, R. A. Grotefendt, C. E. Bowlby, M. L. Bonnell, and K. C. Balcomb, III. 

1992. Cetacean distribution and abundance off Oregon and Washington. Ch. 1. In: Oregon and 

Washington Marine Mammal and Seabird Surveys. OCS Study 91-0093. Final Report prepared 

for Pacific OCS Region, Minerals Management Service, U.S. Department of the Interior, Los 

Angeles, California. 

Green, G., R. A. Grotefendt, M. A. Smultea, C. E. Bowlby, and R. A. Rowlett. 1993. Delphinid aerial 

surveys in Oregon and Washington waters. Final Report prepared for NMFS, National Marine 

Mammal Laboratory, 7600 Sand Point Way, NE, Seattle, Washington, 98115, Contract 

#50ABNF200058. 

Holts, D. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La Jolla, 

CA 92038. 

Holts, D. and O. Sosa-Nishizaki. 1998. Swordfish, Xiphias gladius, fisheries of the eastern North Pacific 

Ocean. In: I. Barrett, O. Sosa-Nishizaki and N. Bartoo (eds.). Biology and fisheries of swordfish, 

Xiphias gladius. Papers from the International Symposium on Pacific Swordfish, Ensenada 

Mexico, 11-14 December 1994. U.S. Dep. Commer., NOAA Tech. Rep. NMFS 142, 276 pp. 

85
Julian, F. and M. Beeson. 1998. Estimates of mammal, turtle and bird mortality for two California gillnet 

fisheries: 1990-1995. Fish. Bull. 96:271-284. 

Mangels, K. F. and Gerrodette, T. 1994. Report of cetacean sightings during a marine mammal survey in 

the eastern Pacific Ocean and Gulf of California aboard the NOAA ships McARTHUR and DAVID 

STARR JORDAN July 28 - November 6, 1993. U.S. Dep. Commer. NOAA Tech. Memo. NMFSSWFSC-211. 88 pp. 

Morejohn, G. V. 1979. The natural history of Dall's porpoise in the North Pacific Ocean. In: Winn, H. 

E. and B. L. Olla (eds.), Behavior of Marine Mammals, p. 45-83. Plenum Press, New York - 

London. 

Perez, M. A. and T. R. Loughlin. 1991. Incidental catch of marine mammals by foreign and joint venture 

trawl vessels in the U.S. EEZ of the North Pacific, 1973-88. U.S. Dep. Commer. NOAA Tech. 

Rep. 104. 57 p. 

Perez, M. 2003. Compilation of marine mammal incidental take data from the domestic and joint venture 

groundfish fisheries in the U.S. EEZ of the North Pacific, 1989-2001. U.S. Dep. Commer., 

NOAA Tech. Memo. NMFS-AFSC-138. 145 pp. 

Perrin, W. F. and R. L. Brownell, Jr. 1994. A brief review of stock identity in small marine cetaceans in 

relation to assessment of driftnet mortality in the North Pacific. Rep. Int. Whal. Commn. Special 

Issue 15:393-401. 

Sosa-Nishizaki, O., R. De la Rosa Pacheco, R. Castro Longoria, M. Grijalva Chon, and J. De la Rosa 

Velez. 1993. Estudio biologico pesquero del pez (Xiphias gladius) y otras especies de picudos 

(marlins y pez vela). Rep. Int. CICESE, CTECT9306. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the 

GAMMS Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. 

Memo. NMFS-OPR-12. 93 pp. 

86
Revised 10/30/2007

PACIFIC WHITE-SIDED DOLPHIN (Lagenorhynchus obliquidens): 

California/Oregon/Washington, Northern and Southern Stocks 

STOCK DEFINITION AND GEOGRAPHIC RANGE

 Pacific white-sided dolphins 

are endemic to temperate waters of 

the North Pacific Ocean, and are 

common both on the high seas and 

along the continental margins. Off 

the U.S. west coast, Pacific whitesided dolphins have been seen 

primarily in shelf and slope waters 

(Figure 1). Sighting patterns from 

recent aerial and shipboard surveys 

conducted in California, Oregon and 

Washington at different times of the 

year (Green et al. 1992; 1993; Barlow 

1995; Forney et al. 1995) suggest 

seasonal north-south movements, 

with animals found primarily off 

California during the colder water 

months and shifting northward into 

Oregon and Washington as water 

temperatures increase in late spring 

and summer (Green et al. 1992; 

Forney 1994). 

 Stock structure throughout 

the North Pacific is poorly 

understood, but based on 

morphological evidence, two forms 

are known to occur off the California 

coast (Walker et al. 1986; Chivers et 

al. 1993). Specimens belonging to 

the northern form were collected from 

north of about 33o

N, (Southern 

California to Alaska), and southern 

specimens were obtained from about 36o

N 

southward along the coasts of California and 

Baja California. Samples of both forms 

have been collected in the Southern 

California Bight, but it is unclear whether 

this indicates sympatry in this region or 

whether they may occur there at different 

times (seasonally or interannually). Recent 

genetic analyses have confirmed the 

distinctness of animals found off Baja 

California from animals occurring in U.S. waters north of Point Conception, California and in the high seas 

of the North Pacific (Lux et al. 1997). Based on these genetic data, an area of mixing between the two 

forms appears to be located off Southern California (Lux et al. 1997). 

OREGON

WASHINGTON

CALIFORNIA

 Although there is clear evidence that two forms of Pacific white-sided dolphins occur along the 

U.S. west coast, there are no known differences in color pattern, and it is not currently possible to 

distinguish animals without genetic or morphometric analyses. Geographic stock boundaries appear 

dynamic and are poorly understood, and therefore cannot be used to differentiate the two forms. Until 

Figure 1. Pacific white-sided dolphin sightings 

based on aerial and shipboard surveys off 

California, Oregon, and Washington, 1991- 2005 

(see Appendix 2 for data sources and information 

on timing and location of survey effort). Dashed 

line represents the U.S. EEZ, thin lines indicate 

completed transect effort of all surveys combined. 

Key: • = summer/autumn ship-based sightings; + 

= winter/spring aerial-based sightings. 

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

45°0'0"N

40°0'0"N

87
means of differentiating the two forms for abundance and mortality estimation are developed, these two 

stocks must be managed as a single unit; however, this is an undesirable management situation. 

Furthermore, Pacific white-sided dolphins are not restricted to U.S. territorial waters, but cooperative 

management agreements with Mexico exist only for the tuna purse seine fishery and not for other fisheries 

which may take this species (e.g. gillnet fisheries). Additional means of differentiating the two types must 

be found, and cooperative management with Mexico is particularly important for this species, given the 

apparently dynamic nature of geographical stock boundaries. Until these goals are accomplished, the 

management stock includes animals of both forms. For the Marine Mammal Protection Act (MMPA) stock 

assessment reports, Pacific white-sided dolphins within the Pacific U.S. Exclusive Economic Zone are 

divided into two discrete, non-contiguous areas: 1) waters off California, Oregon and Washington (this 

report), and 2) Alaskan waters. 

POPULATION SIZE

 The most recent estimates of abundance for Pacific white-sided dolphins are based on two 

summer/autumn shipboard surveys conducted within 300 nmi of the coasts of California, Oregon, and 

Washington in 2001 and 2005 (Barlow 2003; Forney 2007). The distribution of Pacific white-sided 

dolphins throughout this region is highly variable, apparently in response to oceanographic changes on both 

seasonal and interannual time scales (Forney and Barlow 1998). As oceanographic conditions vary, Pacific 

white-sided dolphins may spend time outside the U.S. Exclusive Economic Zone, and therefore a multiyear average abundance estimate including California, Oregon and Washington is the most appropriate for 

management within U.S. waters. The 2001-2005 geometric mean abundance estimate for California, 

Oregon and Washington waters based on the two most recent ship surveys is 25,233 (CV = 0.25) Pacific 

white-sided dolphins (Forney 2007). 

Minimum Population Estimate

 The log-normal 20th percentile of the 2001-2005 average abundance estimate is 20,441 Pacific 

white-sided dolphins. 

Current Population Trend

 No long-term trends in the abundance of Pacific white-sided dolphins in California, Oregon and 

Washington are suggested based on historical and recent surveys (Dohl et al. 1980; 1983; Green et al. 1992; 

1993; Barlow 1995; Forney et al. 1995, Barlow 2003, Forney 2007). 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No information on current or maximum net productivity rates is available for Pacific white-sided 

dolphins off the U.S. west coast. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum 

population size (20,441) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times

a recovery factor of 0.45 (for a species of unknown status with a mortality rate CV > 0.60 and ≤0.80; Wade 

and Angliss 1997), resulting in a PBR of 184 Pacific white-sided dolphins per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information 

 A summary of recent fishery mortality and injury for this stock of Pacific white-sided dolphin is 

shown in Table 1. More detailed information on these fisheries is provided in Appendix 1. Mortality 

estimates for the California drift gillnet fishery are included for the five most recent years of monitoring, 

2000-2004 (Carretta and Chivers 2004, Carretta et al. 2005a, 2005b). After the 1997 implementation of a 

Take Reduction Plan, which included skipper education workshops and required the use of pingers and 

minimum 6-fathom extenders, overall cetacean entanglement rates in the drift gillnet fishery dropped 

considerably (Barlow and Cameron 2003). However, because of interannual variability in entanglement 

rates and the relative rarity of Pacific white-sided dolphin entanglements, additional years of data will be 

required to fully evaluate the effectiveness of pingers for reducing mortality of this particular species. 

Mean annual takes in Table 1 are based on 2000-2004 data. Including mortality from drift gillnet, 

88
groundfish trawl, and unknown fisheries, the average annual fishery-related mortality of Pacific whitesided dolphins in 2000-2004 is 5.6 (CV = 0.72) animals. 

 Drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of Baja 

California, Mexico and may take animals from this population. Quantitative data are available only for the 

Mexican swordfish drift gillnet fishery, which uses vessels, gear, and operational procedures similar to 

those in the U.S. drift gillnet fishery, although nets may be up to 4.5 km long (Holts and Sosa-Nishizaki 

1998). The fleet increased from two vessels in 1986 to 31 vessels in 1993 (Holts and Sosa-Nishizaki 1998). 

The total number of sets in this fishery in 1992 can be estimated from data provided by these authors to be 

approximately 2700, with an observed rate of marine mammal bycatch of 0.13 animals per set (10 marine 

mammals in 77 observed sets; Sosa-Nishizaki et al. 1993). This overall mortality rate is similar to that 

observed in California driftnet fisheries during 1990-95 (0.14 marine mammals per set; Julian and Beeson, 

1998), but species-specific information is not available for the Mexican fisheries. Previous efforts to 

convert the Mexican swordfish driftnet fishery to a longline fishery have resulted in a mixed-fishery, with 

20 vessels alternately using longlines or driftnets, 23 using driftnets only, 22 using longlines only, and 

seven with unknown gear type (Berdegué 2002). 

Table 1. Summary of available information on the incidental mortality and injury of Pacific white-sided 

dolphins (California/ Oregon/Washington Stock) in commercial fisheries that might take this species. All 

observed entanglements of Pacific white-sided dolphins resulted in the death of the animal. Coefficients of 

variation for mortality estimates are provided in parentheses; n/a = not available. Mean annual takes are 

based on 2000-2004 data unless noted otherwise. 

Fishery Name Data Type Year(s) 

Percent 

Observer 

Coverage

Observed 

Mortality

Estimated Annual 

Mortality

Mean Annual 

Takes (CV in 

parentheses)

CA/OR thresher 

shark/swordfish drift 

gillnet fishery

observer data 

2000 

2001 

2002 

2003 

2004 

22.9% 

20.4% 

22.1% 

20.2% 

20.6% 

2 

2 

1 

0 

0 

9 ( 0.68) 

10( 0.71) 

5 (0.86) 

0 

0 

4.8 (0.72) 

WA/OR/CA domestic 

groundfish trawl fisheries

(At-sea processing Pacific 

whiting fishery only).

observer data 

2000 

2001 

2002 

2003 

2004 

80.6% 

96.2% 

100% 

100% 

100% 

0 

0 

0 

1 

0 

0 

0 

0 

1 (n/a) 

0 

0.2 n/a) 

Unknown fishery stranding 

2000 

2001 

2002 

2003 

2004 

0 

2 

0 

0 

1 

n/a ≥0.6 

Minimum total annual takes 5.6 (0.72) 

 Low levels of mortality for Pacific white-sided dolphins have also been documented in the 

California/Oregon/ Washington domestic groundfish trawl fisheries (Perez and Loughlin 1991; Perez, in 

prep;). Between 2000-2004, with 80-100% of the fishing effort observed, one Pacific white-sided dolphin 

was reported killed in the at-sea processing portion of the Pacific whiting trawl fishery (NMFS,unpublished 

data). Fishery-related strandings of Pacific white-sided dolphins in California/Oregon/Washington between 

2000-2004 totalled 3 animals (Table 1). In 2001, two white-sided dolphins stranded in southern Californa 

within a week, one animal had its flukes cut off, the second animal had yellow nylon line around the caudal 

peduncle and apparent bullet holes on each side of the head. A third animal stranded in 2004 with net-like 

markings. 

Other removals

 Additional removals of Pacific white-sided dolphins from the wild have occurred in live-capture 

fisheries off California. Brownell et al. (1999) estimate a minimum total live capture of 128 Pacific whitesided dolphins between the late 1950s and 1993. The most recent capture was in November 1993, when 

89
three animals were taken for public display (Forney 1994). No MMPA permits are currently active for 

live-captures of Pacific white-sided dolphins. 

STATUS OF STOCK

 The status of Pacific white-sided dolphins in California, Oregon and Washington relative to OSP 

is not known, and there is no indication of a trend in abundance for this stock. No habitat issues are known 

to be of concern for this species. They are not listed as "threatened" or "endangered" under the Endangered 

Species Act nor as "depleted" under the MMPA. The average annual human-caused mortality in 2000-

2004 (5.6 animals) is estimated to be less than the PBR (184), and therefore they are not classified as a 

"strategic" stock under the MMPA. The total fishery mortality and serious injury for this stock is less than 

10% of the calculated PBR and, therefore, can be considered to be insignificant and approaching zero 

mortality and serious injury rate. 

REFERENCES

Barlow, J. 1995. The abundance of cetaceans in California waters. Part I: Ship surveys in summer and fall 

of 1991. Fish. Bull. 93:1-14. 

Barlow, J. 1997. Preliminary estimates of cetacean abundance off California, Oregon and Washington 

based on a 1996 ship survey and comparisons of passing and closing modes. Admin. Rep. LJ-97-

11, Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 25p. 

Barlow, J. and G. A. Cameron. 2003. Field experiments show that acoustic pingers reduce marine mammal 

bycatch in the California drift gillnet fishery. Marine Mammal Science 19(2):265-283. 

Barlow, J. and T. Gerrodette. 1996. Abundance of cetaceans in California waters based on 1991 and 1993 

ship surveys. NOAA Tech. Memo. NMFS-SWFSC-233. 15 pp. 

Barlow, J., K. A. Forney, P. S. Hill, R. L. Brownell, Jr., J. V. Carretta, D. P. DeMaster, F. Julian, M. S. 

Lowry, T. Ragen, and R. R. Reeves. 1997. U.S. Pacific Marine Mammal Stock Assessments: 

1996. U.S. Dep. Commer., NOAA Tech. Memo. NMFS-SWFSC-248. 223 pp. 

Barlow, J. 2003. Preliminary estimates of the abundance of cetaceans along the U.S. west coast: 

1991_2001. Southwest Fisheries Science Center Administrative Report LJ_03_03. Available 

from SWFSC, 8604 La Jolla Shores Dr., La Jolla CA 92037. 31p. 

Berdegué, J. 2002. Depredación de las especies pelágicas reservadas a la pesca deportiva y especies en 

peligro de extinción con uso indiscriminado de artes de pesca no selectivas (palangres, FAD's, 

trampas para peces y redes de agallar fijas y a la deriva) por la flota palangrera Mexicana. 

Fundación para la conservación de los picudos. A.C. Mazatlán, Sinaloa, 21 de septiembre. 

Brownell, R. L., Jr., W. A. Walker and K. A. Forney. 1999. Pacific white-sided dolphin, Lagenorhynchus 

obliquidens Gill, 1865. Pages 57-84 In: Ridgway, S. H. and R. Harrison (eds.), Handbook of 

Marine Mammals, Vol. 6. Academic Press, San Diego. 

Carretta, J.V. and S.J. Chivers. 2004. Preliminary estimates of marine mammal mortality and biological 

sampling of cetaceans in California gillnet fisheries for 2003. Paper SC/56/SM1 presented to the 

IWC Scientific Committee, June 2004 (unpublished). [Available from Southwest Fisheries 

Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 

92037, USA]. 

Carretta, J.V., S.J. Chivers, and K. Danil. 2005a. Preliminary estimates of marine mammal bycatch, 

mortality, and biological sampling of cetaceans in California gillnet fisheries for 2004. 

Administrative Report LJ-05-10, available from Southwest Fisheries Science Center, 8604 La 

Jolla Shores Drive, La Jolla, California, 92037. 17 p. 

Carretta, J.V., T. Price, D. Petersen, and R. Read. 2005b. Estimates of marine mammal, sea turtle, and 

seabird mortality in the California drift gillnet fishery for swordfish and thresher shark, 1996-

2002. Marine Fisheries Review 66(2):21-30. 

Chivers, S. J., K. M. Peltier, W. T. Norman, P. A. Akin, and J. Heyning. 1993. Population structure of 

cetaceans in California coastal waters. Paper SOCCS9 presented at the Status of California 

Cetacean Stocks Workshop, held in La Jolla, California, March 31-April 2, 1993. 49p. 

Dohl, T. P., R. C. Guess, M. L. Duman, and R. C. Helm. 1983. Cetaceans of central and northern 

California, 1980-1983: Status, abundance and distribution. OCS Study MMS 84-0045. Minerals 

Management Service Contract # 14-12-0001-29090. 284p. 

90
Dohl, T. P., K. S. Norris, R. C. Guess, J. D. Bryant, and M. W. Honig. 1980. Summary of marine mammal 

and seabird surveys of the Southern California Bight area, 1975-1978. Part II. Cetacea of the 

Southern California Bight. Final Report to the Bureau of Land Management, NTIS Rep. No. 

PB81248189. 414p. 

Forney, K. A. 1994. Recent information on the status of odontocetes in Californian waters. U.S. Dep. 

Commer., NOAA Tech. Memo. NMFS-SWFSC-202. 87 pp. 

Forney, K. A. 1997. Patterns of variability and environmental models of relative abundance for California 

cetaceans. Ph.D. dissertation, Scripps Institution of Oceanography, University of California, San 

Diego. 

Forney, K. A. and J. Barlow. 1998. Seasonal patterns in the abundance and distribution of California 

cetaceans, 1991-92. Mar. Mamm. Sci. 14:460-489. 

Forney, K. A., J. Barlow and J. V. Carretta. 1995. The abundance of cetaceans in California waters. Part 

II: Aerial surveys in winter and spring of 1991 and 1992. Fish. Bull. 93:15-26. 

Forney, K.A. 2007. Preliminary estimates of cetacean abundance along the U.S. west coast and within 

four National Marine Sanctuaries during 2005. U.S. Department of Commerce, NOAA Technical 

Memorandum NMFS-SWFSC-xxx. 

Green, G., J. J. Brueggeman, R. A. Grotefendt, C. E. Bowlby, M. L. Bonnell, and K. C. Balcomb, III. 

1992. Cetacean distribution and abundance off Oregon and Washington. Ch. 1. In: Oregon and 

Washington Marine Mammal and Seabird Surveys. OCS Study 91-0093. Final Report prepared 

for Pacific OCS Region, Minerals Management Service, U.S. Department of the Interior, Los 

Angeles, California. 

Green, G., R. A. Grotefendt, M. A. Smultea, C. E. Bowlby, and R. A. Rowlett. 1993. Delphinid aerial 

surveys in Oregon and Washington waters. Final Report prepared for NMFS, National Marine 

Mammal Laboratory, 7600 Sand Point Way, NE, Seattle, Washington, 98115, Contract 

#50ABNF200058. 

Holts, D. and O. Sosa-Nishizaki. 1998. Swordfish, Xiphias gladius, fisheries of the eastern North Pacific 

Ocean. In: I. Barrett, O. Sosa-Nishizaki and N. Bartoo (eds.). Biology and fisheries of swordfish, 

Xiphias gladius. Papers from the International Symposium on Pacific Swordfish, Ensenada 

Mexico, 11-14 December 1994. U.S. Dep. Commer., NOAA Tech. Rep. NMFS 142. 276 pp. 

Julian, F. and M. Beeson. 1998. Estimates of mammal, turtle and bird mortality for two California gillnet 

fisheries: 1990-1995. Fish. Bull. 96:271-284. 

Lux, C. A., A. S. Costa, and A. E. Dizon. 1997. Mitochondrial DNA population structure of the Pacific 

white-sided dolphin. Rep. Int. Whaling. Commn. 47:645-652. 

Perez, M. A. and T. R. Loughlin. 1991. Incidental catch of marine mammals by foreign and joint venture 

trawl vessels in the U.S. EEZ of the North Pacific, 1973-88. NOAA Tech. Rep. NMFS 104. 57 

pp. 

Perez, M. A. (in prep). Summary of marine mammal incidental catch data for domestic and joint venture 

groundfish fisheries in the U.S. EEZ of the North Pacific, 1989-2001. NOAA Tech. Memo. 

Sosa-Nishizaki, O., R. De la Rosa Pacheco, R. Castro Longoria, M. Grijalva Chon, and J. De la Rosa 

Velez. 1993. Estudio biologico pesquero del pez (Xiphias gladius) y otras especies de picudos 

(marlins y pez vela). Rep. Int. CICESE, CTECT9306. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the 

GAMMS Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. 

Memo. NMFS-OPR-12. 93 pp. 

Walker, W. A., S. Leatherwood, K. R. Goodrich, W. F. Perrin and R. K. Stroud. 1986. Geographical 

variation and biology of the Pacific white-sided dolphin, Lagenorhynchus obliquidens, in the 

north-eastern Pacific. In: Bryden, M. M. and R. Harrison (eds.), Research on Dolphins, p. 441-

465. Clarendon Press, Oxford. 

91
Revised 10/30/2007

RISSO'S DOLPHIN (Grampus griseus): 

California/Oregon/Washington Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

 Risso's dolphins are 

distributed world-wide in tropical 

and warm-temperate waters. Off 

the U.S. West coast, Risso's 

dolphins are commonly seen on the 

shelf in the Southern California 

Bight and in slope and offshore 

waters of California, Oregon and 

Washington. Based on sighting 

patterns from recent aerial and 

shipboard surveys conducted in 

these three states during different 

seasons (Figure 1), animals found 

off California during the colder 

water months are thought to shift 

northward into Oregon and 

Washington as water temperatures 

increase in late spring and summer 

(Green et al. 1992). The southern 

end of this population's range is not 

well-documented, but previous 

surveys have shown a conspicuous 

500 nmi distributional gap between 

these animals and Risso's dolphins 

sighted south of Baja California and 

in the Gulf of California (Mangels 

and Gerrodette 1994). Thus this 

population appears distinct from 

animals found in the eastern tropical 

Pacific and the Gulf of California. 

Although Risso's dolphins are not 

restricted to U.S. waters, cooperative 

management agreements with Mexico 

exist only for the tuna purse seine fishery 

and not for other fisheries which may take 

this species (e.g. gillnet fisheries). For the 

Marine Mammal Protection Act (MMPA) 

stock assessment reports, Risso's dolphins 

within the Pacific U.S. Exclusive 

Economic Zone are divided into two 

discrete, non-contiguous areas: 1) waters off California, Oregon and Washington (this report), and 2) 

Hawaiian waters.

OREGON

WASHINGTON

CALIFORNIA

POPULATION SIZE

 The previous best estimates of abundance for Risso’s dolphins were based on three 

summer/autumn shipboard surveys conducted within 300 nmi of the coasts California in 1991 and 1993 

(Barlow and Gerrodette 1996) and California, Oregon, and Washington in 1996 (Barlow 1997). More 

recently, two shipboard surveys within 300 nmi of the coasts of California, Oregon, and Washington were 

conducted in summer/autumn of 2001 (Barlow, 2003) and 2005 (Forney, 2007). The distribution of 

Figure 1. Risso’s dolphin sightings based on aerial 

and shipboard surveys off California, Oregon, and 

Washington, 1991-2005 (see Appendix 2 for data 

sources and information on timing and location of 

survey effort). Dashed line represents the U.S. 

EEZ, thin lines indicate completed transect effort of 

all surveys combined. Key: • = summer/autumn 

ship-based sightings; + = winter/spring aerial-based 

sightings. 

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

45°0'0"N

40°0'0"N

92
Risso’s dolphins throughout this region is highly variable, apparently in response to oceanographic changes 

on both seasonal and interannual time scales (Forney and Barlow 1998). As oceanographic conditions 

vary, Risso’s dolphins may spend time outside the U.S. Exclusive Economic Zone, and therefore a multiyear average abundance estimate is the most appropriate for management within U.S. waters. The 2001-

2005 geometric mean abundance estimate for California, Oregon and Washington waters based on the two 

most recent ship surveys is 12,093 (CV = 0.24) Risso’s dolphins (Barlow 2003, Forney, 2007). 

Minimum Population Estimate

 The log-normal 20th percentile of the 2001-2005 weighted average abundance estimate is 9,947 

Risso's dolphins. 

Current Population Trend

 The pooled abundance estimate from the most recent two surveys of California, Oregon, and 

Washington waters is 12,093 (CV=0.24), which is not significantly different from the estimate of 16,066 

(0.28) from pooled 1996-2001 surveys (Barlow 2003). Inter-annual variability in the distribution of 

Risso’s dolphin within the ship survey study area is likely responsible for the differences in estimated 

abundance between surveys. Currently, there is no evidence of a trend in abundance for this stock. 

 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No information on current or maximum net productivity rates is available for this stock. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum 

population size (9,947) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times

a recovery factor of 0.40 (for a species of unknown status with a mortality rate CV >0.80; Wade and 

Angliss 1997), resulting in a PBR of 80 Risso’s dolphins per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

 A summary of recent fishery mortality and injury for this stock of Risso’s dolphin is shown in 

Table 1. More detailed information on these fisheries is provided in Appendix 1. Mortality estimates for 

the California drift gillnet fishery are included for the five most recent years of monitoring, 2000-2004 

(Carretta and Chivers 2004 ; Carretta et al. 2005a, 2005b). After the 1997 implementation of a Take 

Reduction Plan, which included skipper education workshops and required the use of pingers and minimum 

6-fathom extenders, overall cetacean entanglement rates in the drift gillnet fishery dropped considerably 

(Barlow and Cameron 2003). However, because of interannual variability in entanglement rates and the 

relative rarity of Risso’s dolphin entanglements, additional years of data will be required to fully evaluate 

the effectiveness of pingers for reducing mortality of this particular species. Additional mortality and 

injury information from the former California shallow set longline fishery and unknown fishery-related 

strandings are included in Table 1. Mean annual takes in Table 1 are based on 2000-2004 data. This results 

in an average estimate 6.6 (CV = 1.02) Risso’s dolphins taken annually. 

Table 1. Summary of available information on the incidental mortality and injury of Risso's dolphin 

(California/ Oregon/Washington Stock) in commercial fisheries that might take this species. All observed 

entanglements of Risso's dolphins resulted in the death of the animal. Coefficients of variation for mortality 

estimates are provided in parentheses; n/a = not available. Mean annual takes are based on 2000-2004 data 

unless noted otherwise. 

Fishery Name Data Type

Year(s) 

Percent 

Observer 

Coverage

Observed

Mortality

Estimated Annual 

Mortality 

(CV)

Mean Annual 

Takes (CV)

CA/OR thresher 

shark/swordfish drift gillnet 

fishery

observer 

2000 

2001 

2002 

2003 

2004 

22.9% 

20.4% 

22.1% 

20.2% 

20.6% 

2 

0 

0 

4 

0 

9 (0.71) 

0 

0 

20 (0.50) 

0

5.8 (1.02)

93
Fishery Name Data Type

Year(s) 

Percent 

Observer 

Coverage

Observed 

Mortality

Estimated Annual 

Mortality 

(CV)

Mean Annual 

Takes (CV)

CA shallow set longline 

fishery observer 

2001 

2002 

2003 

2004 

No fishery 

in 2005 

n/a 

1 animal 

released 

injured in 

2003, hook 

not removed 

n/a 0.25 (n/a) 

Unknown fishery stranding 

2002 

2003 

2 

1 

n/a 

n/a 

0.6 (n/a) 

Minimum total annual takes 6.6 (1.02) 

 

 Drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of Baja 

California, Mexico and may take animals from this population. Quantitative data are available only for the 

Mexican swordfish drift gillnet fishery, which uses vessels, gear, and operational procedures similar to 

those in the U.S. drift gillnet fishery, although nets may be up to 4.5 km long (Holts and Sosa-Nishizaki 

1998). The fleet increased from two vessels in 1986 to 31 vessels in 1993 (Holts and Sosa-Nishizaki 1998). 

The total number of sets in this fishery in 1992 can be estimated from data provided by these authors to be 

approximately 2700, with an observed rate of marine mammal bycatch of 0.13 animals per set (10 marine 

mammals in 77 observed sets; Sosa-Nishizaki et al. 1993). This overall mortality rate is similar to that 

observed in California driftnet fisheries during 1990-95 (0.14 marine mammals per set; Julian and Beeson, 

1998), but species-specific information is not available for the Mexican fisheries. Previous efforts to 

convert the Mexican swordfish driftnet fishery to a longline fishery have resulted in a mixed-fishery, with 

20 vessels alternately using longlines or driftnets, 23 using driftnets only, 22 using longlines only, and 

seven with unknown gear type (Berdegué 2002). 

 Additional mortality of unknown extent has been documented for Risso's dolphins in the squid 

purse seine fishery off Southern California (Heyning et al. 1994). This mortality probably represented 

animals killed intentionally to protect catch or gear, rather than incidental mortality, and such intentional 

takes are now illegal under the 1994 Amendment to the MMPA. This fishery has expanded markedly since 

1992 (California Department of Fish and Game, unpubl. data). In addition to mortalities observed in the 

drift gillnet fishery, there were three fishery-related strandings of Risso’s dolphin during 2000-2004. 

Bullets or bullet fragments were removed from two of the three animals while the third animal showed 

evidence of gunshot wounds. Two animals had recently been feeding on squid. The timing, circumstances 

and location of the strandings suggests that the squid purse seine fishery may have been responsible for the 

mortalities. 

STATUS OF STOCK

 The status of Risso's dolphins off California, Oregon and Washington relative to OSP is not 

known, and there are insufficient data to evaluate potential trends in abundance. No habitat issues are 

known to be of concern for this species. They are not listed as "threatened" or "endangered" under the 

Endangered Species Act nor as "depleted" under the MMPA. Over the last 5-year period (2000-2004), the 

average annual human-caused mortality (6.6 animals) is estimated to be less than the PBR (80), and 

therefore they are not classified as a "strategic" stock under the MMPA. The total fishery mortality and 

serious injury for this stock is less than 10% of the calculated PBR and, therefore, can be considered to be 

insignificant and approaching zero mortality and serious injury rate. 

 

REFERENCES

Barlow, J. 1997. Preliminary estimates of cetacean abundance off California, Oregon and Washington 

based on a 1996 ship survey and comparisons of passing and closing modes. Admin. Rep. LJ-97-

11, Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 25p. 

Barlow, J. and G. A. Cameron. 2003. Field experiments show that acoustic pingers reduce marine mammal 

bycatch in the California drift gillnet fishery. Marine Mammal Science 19(2):265-283. 

94
Barlow, J., K. A. Forney, P. S. Hill, R. L. Brownell, Jr., J. V. Carretta, D. P. DeMaster, F. Julian, M. S. 

Lowry, T. Ragen, and R. R. Reeves. 1997. U.S. Pacific Marine Mammal Stock Assessments: 

1996. U.S. Dep. Commer., NOAA Tech. Memo. NMFS-SWFSC-248. 223p. 

Barlow, J. and T. Gerrodette. 1996. Abundance of cetaceans in California waters based on 1991 and 1993 

ship surveys. NOAA Tech. Memo. NMFS-SWFSC-233. 15 pp. 

Barlow, J. 1997. Preliminary estimates of cetacean abundance off California, Oregon, and Washington 

based on a 1996 ship survey and comparisons of closing and passing modes. Administrative 

Report LJ-97-11, Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92037. 25p. 

Barlow, J. 2003. Preliminary estimates of the abundance of cetaceans along the U.S. west coast: 

1991_2001. Southwest Fisheries Science Center Administrative Report LJ_03_03. Available 

from SWFSC, 8604 La Jolla Shores Dr., La Jolla CA 92037. 31p. 

Berdegué, J. 2002. Depredación de las especies pelágicas reservadas a la pesca deportiva y especies en 

peligro de extinción con uso indiscriminado de artes de pesca no selectivas (palangres, FAD's, 

trampas para peces y redes de agallar fijas y a la deriva) por la flota palangrera Mexicana. 

Fundación para la conservación de los picudos. A.C. Mazatlán, Sinaloa, 21 de septiembre. 

Carretta, J.V. and S.J. Chivers. 2004. Preliminary estimates of marine mammal mortality and biological 

sampling of cetaceans in California gillnet fisheries for 2003. Paper SC/56/SM1 presented to the 

IWC Scientific Committee, June 2004 (unpublished). [Available from Southwest Fisheries 

Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 

92037, USA]. 

Carretta, J.V., S.J. Chivers, and K. Danil. 2005a. Preliminary estimates of marine mammal bycatch, 

mortality, and biological sampling of cetaceans in California gillnet fisheries for 2004. 

Administrative Report LJ-05-10, available from Southwest Fisheries Science Center, 8604 La 

Jolla Shores Drive, La Jolla, California, 92037. 17 p. 

Carretta, J.V., T. Price, D. Petersen, and R. Read. 2005b. Estimates of marine mammal, sea turtle, and 

seabird mortality in the California drift gillnet fishery for swordfish and thresher shark, 1996-

2002. Marine Fisheries Review 66(2):21-30. 

Forney, K. A. and J. Barlow. 1998. Seasonal patterns in the abundance and distribution of California 

cetaceans, 1991-92. Mar. Mamm. Sci. 14:460-489. 

Forney, K. A., J. Barlow and J. V. Carretta. 1995. The abundance of cetaceans in California waters. Part 

II: Aerial surveys in winter and spring of 1991 and 1992. Fish. Bull. 93:15-26. 

Forney, K.A. 2007. Preliminary estimates of cetacean abundance along the U.S. west coast and within 

four National Marine Sanctuaries during 2005. U.S. Department of Commerce, NOAA Technical 

Memorandum NMFS-SWFSC-406. 27 p. 

Green, G., J. J. Brueggeman, R. A. Grotefendt, C. E. Bowlby, M. L. Bonnell, and K. C. Balcomb, III. 

1992. Cetacean distribution and abundance off Oregon and Washington. Ch. 1. In: Oregon and 

Washington Marine Mammal and Seabird Surveys. OCS Study 91-0093. Final Report prepared 

for Pacific OCS Region, Minerals Management Service, U.S. Department of the Interior, Los 

Angeles, California. 

Green, G., R. A. Grotefendt, M. A. Smultea, C. E. Bowlby, and R. A. Rowlett. 1993. Delphinid aerial 

surveys in Oregon and Washington waters. Final Report prepared for NMFS, National Marine 

Mammal Laboratory, 7600 Sand Point Way, NE, Seattle, Washington, 98115, Contract 

#50ABNF200058. 

Heyning, J. E., T. D. Lewis and C. D. Woodhouse. 1994. A note on odontocete mortality from fishing 

gear entanglements off Southern California. Rep. Int. Whal. Commn. Special Issue 15:439-442. 

Holts, D. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La Jolla, 

CA 92038. 

Holts, D. and O. Sosa-Nishizaki. 1998. Swordfish, Xiphias gladius, fisheries of the eastern North Pacific 

Ocean. In: I. Barrett, O. Sosa-Nishizaki and N. Bartoo (eds.). Biology and fisheries of swordfish, 

Xiphias gladius. Papers from the International Symposium on Pacific Swordfish, Ensenada 

Mexico, 11-14 December 1994. U.S. Dep. Commer., NOAA Tech. Rep. NMFS 142, 276 p. 

Julian, F. and M. Beeson. 1998. Estimates of mammal, turtle and bird mortality for two California gillnet 

fisheries: 1990-1995. Fish. Bull. 96:271-284. 

Mangels, K. F. and Gerrodette, T. 1994. Report of cetacean sightings during a marine mammal survey in 

the eastern Pacific Ocean and Gulf of California aboard the NOAA ships McARTHUR and DAVID 

95
STARR JORDAN July 28 - November 6, 1993. U.S. Dep. Commer., NOAA Tech. Memo. NMFSSWFSC-211. 88 pp. 

Shane, S. 1994. Occurrence and habitat use of marine mammals at Santa Catalina Island, California from 

1983-91. Bull. Southern California Acad. Sci. 93:13-29. 

Sosa-Nishizaki, O., R. De la Rosa Pacheco, R. Castro Longoria, M. Grijalva Chon, and J. De la Rosa 

Velez. 1993. Estudio biologico pesquero del pez (Xiphias gladius) y otras especies de picudos 

(marlins y pez vela). Rep. Int. CICESE, CTECT9306. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the 

GAMMS Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commerce, NOAA Tech. 

Memo. NMFS-OPR-12. 93 pp. 

96
Revised 12/15/2006

BOTTLENOSE DOLPHIN (Tursiops truncatus): 

California Coastal Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

Bottlenose dolphins are distributed worldwide in tropical and warm-temperate waters. In 

many regions, including California, separate coastal 

and offshore populations are known (Walker 1981; 

Ross and Cockcroft 1990; Van Waerebeek et al. 

1990). Based on nuclear and mtDNA analyses, 

Lowther (2006) identified 5 haplotypes from 29 

coastal animals and 25 haplotypes from 40 offshore 

animals from the U.S. west coast. There were no 

shared haplotypes between coastal and offshore 

animals and significant genetic differentiation 

between the two ecotypes was evident. California 

coastal bottlenose dolphins are found within about 

one kilometer of shore (Figure 1; Hansen, 1990; 

Carretta et al. 1998; Defran and Weller 1999) 

primarily from Point Conception south into Mexican 

waters, at least as far south as San Quintin, Mexico. 

In southern California, animals are found within 500 

m of the shoreline 99% of the time and within 250 

m 90% of the time (Hanson and Defran 1993). 

Oceanographic events appear to influence the 

distribution of animals along the coasts of California 

and Baja California, Mexico, as indicated by a 

change in residency patterns along Southern 

California and a northward range extension into 

central California after the 1982-83 El Niño 

(Hansen and Defran 1990; Wells et al. 1990). 

Since the 1982-83 El Niño, which increased 

water temperatures off California, they have 

been consistently sighted in central California as 

far north as San Francisco. Photo-identification 

studies have documented north-south movements 

of coastal bottlenose dolphins (Hansen 1990; 

Defran et al. 1999), and monthly counts based on surveys between the U.S./Mexican border and Point 

Conception are variable (Carretta et al. 1998), indicating that animals are moving into and out of this area. 

There is little site fidelity of coastal bottlenose dolphins along the California coast; over 80% of the 

dolphins identified in Santa Barbara, Monterey, and Ensenada have also been identified off San Diego 

(Defran et al. 1999, Feinholz 1996, Defran, unpublished data). Although coastal bottlenose dolphins are 

not restricted to U.S. waters, cooperative management agreements with Mexico exist only for the tuna 

purse seine fishery and not for other fisheries which may take this species. Therefore, the management 

stock includes only animals found within U.S. waters. For the Marine Mammal Protection Act (MMPA) 

stock assessment reports, bottlenose dolphins within the Pacific U.S. Exclusive Economic Zone are divided 

into three stocks: 1) California coastal stock (this report), 2) California, Or

W123 W122 W121 W120 W119 W118 W117 W116

N31

N32

N33

N34

N35

N36

N37

N38

N39

N40

San Francisco

Monterey Bay

Point Conception

San Diego

Los Angeles

California

Pacific Ocean

Figure 1. Approximate range (in bold) of 

California coastal bottlenose dolphins based on 

aerial surveys along the coast of California from 

1990-2000. This population of bottlenose dolphins 

is found within about 1 km of shore. 

egon and Washington offshore 

ck, and 3) Hawaiian stock. 

OPUL

population size would be closer to 450-500 animals. Comparing the most recent population size estimate 

sto

P ATION SIZE

 Based on photographic mark-recapture surveys conducted along the San Diego coast in 2004 and 

2005, the most recent estimate of population size is 323 dolphins (CV = 0.13, 95% CI 259-430; Dudzik et 

al. 2005). This estimate does not reflect that approximately 35% of dolphins encountered lack identifiable 

dorsal fin marks (Defran and Weller 1999). If 35% of all animals lack distinguishing marks, then the true 

97
with those obtained from 1987-89 (354 dolphins, 95% CI 330 – 390) and 1996-98 (356 dolphins, 95% CI 

306 – 437; Dudzik 1999) suggests that the population size has been stable for approximately 20 years. 

Older estimates of population size for this stock range from 234 (95% CI 205-263) to 285 (95% CI 265-

306) animals for the period 1985-89 (Defran and Weller 1999). Because coastal bottlenose dolphins 

spend an unknown amount of time in Mexican waters, where they may be subject to mortality in Mexican 

fisheries, an average abundance estimate for California only is the most appropriate for U.S. management 

of this stock. 

Minimum Population Estimate

 The minimum number of dolphins photographically identified during 2004-2005 field studies was 

164, however, the discovery curve for new animals had not yet reached an asymptote during that study 

(Dudzik et al. 2005). The minimum population estimate for this stock is therefore taken as the lower 20th

percentile of the log-normal distribution of abundance obtained from the photographic mark-recapture 

estimate (Dudzik et al. 2005), or approximately 290 dolphins. 

Current Population Trend

 Based on a comparison of mark-recapture abundance estimates for the periods 1987-89 (Nˆ = 354), 

1996-98 (Nˆ = 356), and 2004-05 (Nˆ = 323), Dudzik et al. (2005) stated that the population size had remained 

stable over this period. 

 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No information on current or maximum net productivity rates is available for California coastal 

bottlenose dolphins. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum 

population size (290) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a 

recovery factor of 0.50 (for a species of unknown status with no estimated fishery mortality; Wade and 

Angliss 1997), resulting in a PBR of 2.9 coastal bottlenose dolphins per year. Not all California coastal 

bottlenose dolphins are present in U.S. waters at any given moment and approximately 18% of the stock’s 

range occurs in Mexican waters. Thus, the PBR is prorated by a minimum factor of 0.82 to account for 

time that animals spend outside of U.S. waters. Without additional data on the residence times of dolphins 

in Mexican waters, this factor cannot be improved upon. Because this stock spends some of its time 

outside the U.S. EEZ, the PBR allocation for U.S. waters is 2.9 x 0.82 = 2.4 dolphins per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

 Due to its exclusive use of coastal habitats, this bottlenose dolphin population is susceptible to 

fishery-related mortality in coastal set net fisheries. A summary of information on fishery mortality and 

injury for this stock of bottlenose dolphin is shown in Table 1. More detailed information on the set gillnet 

fishery is provided in Appendix 1. From 1991-94, no bottlenose dolphins were observed taken in this 

fishery with 10-15% observer coverage (Julian and Beeson 1998). The observer program was discontinued 

at the end of 1994, when coastal set gillnet fishing was banned within 3 nmi of the southern California 

coast. In central California, gillnets have been restricted to waters deeper than 30 fathoms (56m) since 

1991 in all areas except between Point Sal and Point Arguello. In 2002, a ban on set gill and trammel nets 

inshore of 60 fathoms from Point Reyes to Point Arguello became effective. Because of these closures, the 

potential for mortality of coastal bottlenose dolphins in the California set gillnet fishery has been greatly 

reduced. Fisher self-report data and 36 stranding records for 1997-2001 do not include any evidence of 

fishery interactions for this stock. In 2003, an immature female bottlenose dolphin stranded dead in San 

Diego, California, with 3.5-inch mesh gillnet wrapped around its tailstock (SWFSC stranding KXD0048). 

Perforation of the animal’s skin suggests the net was on the animal for some time. Mitochondrial DNA 

analysis showed that the haplotype for this animal matches that of known coastal animals (Lowther 2006; 

Lowther et al. in prep). The fishery responsible for this mortality is unknown, but the location and type of 

gillnet found suggests either a set or drift gillnet targeting yellowtail, white seabass, or barracuda. In 2004, 

a bottlenose dolphin with missing flukes washed ashore near Newport Beach, California, suggestive of an 

interaction with an entangling net fishery. The haplotype of this animal matched those of known offshore

98
bottlenose dolphins (Lowther 2006; Lowther et al., in prep). Coastal gillnet fisheries exist in Mexico and 

may take animals from this population, but no details are available. 

 

Table 1. Summary of available information on the incidental mortality and serious injury of bottlenose 

dolphins (California Coastal Stock) in commercial fisheries that might take this species.

Fishery Name Data Type

Year(s) 

Percent 

Observer 

Coverage

Observed

Mortality

Estimated 

Annual 

Mortality

Mean Annual 

Takes (CV in 

parentheses)

CA angel shark/ halibut and 

other species large mesh (>3.5in) 

set gillnet fishery

observer 

data

2000 

2001 

2002 

2003 

2004

1.8%1

0% 

0% 

0% 

0% 

0 0 0

Unknown fishery Stranding 2000-2004 

One bottlenose dolphin with a coastal stock 

haplotype stranded entangled in 3.5-inch mesh 

gillnet in 2003 

≥0.2 (n/a) 

Minimum total annual takes ≥0.2 (n/a) 1

 In 1999 and 2000, approximately 25% of the Monterey Bay portion of the set gillnet fishery was observed, representing <5% of the 

overall fishery. There has been no observer program for this fishery since 2000. 

Other removals

 Seven coastal bottlenose dolphins were collected during the late 1950s in the vicinity of San Diego 

(Norris and Prescott 1961). Twenty-seven additional bottlenose dolphins were captured off California 

between 1966 and 1982 (Walker 1975; Reeves and Leatherwood 1984), but based on the locations of 

capture activities, these animals probably were offshore bottlenose dolphins (Walker 1975). No additional 

captures of coastal bottlenose dolphins have been documented since 1982, and no live-capture permits are 

currently active for this species.

STATUS OF STOCK

 The status of coastal bottlenose dolphins in California relative to OSP is not known, and there is 

no evidence of a trend in abundance. They are not listed as "threatened" or "endangered" under the 

Endangered Species Act nor as "depleted" under the MMPA. Coastal bottlenose dolphins are not classified 

as a "strategic" stock under the MMPA because total annual fishery mortality and serious injury for this 

stock (≥0.2 per year) is less than the PBR (2.4). The total human-caused mortality and serious injury for 

this stock is less than 10% of the calculated PBR and, therefore, can be considered to be insignificant and 

approaching zero. 

Habitat Issues

 Pollutant levels, especially DDT residues, found in Southern California coastal bottlenose 

dolphins have been found to be among the highest of any cetacean examined (O'Shea et al. 1980; Schafer et 

al. 1984). Although the effects of pollutants on cetaceans are not well understood, they may affect 

reproduction or make the animals more prone to other mortality factors (Britt and Howard 1983; O’Shea et 

al. 1999). This population of bottlenose dolphins may also be vulnerable to the effects of morbillivirus 

outbreaks, which were implicated in the 1987-88 mass mortality of bottlenose dolphins on the U.S. Atlantic 

coast (Lipscomb et al. 1994). 

REFERENCES

Britt, J.O. and E. B. Howard. 1983. Tissue residues of selected environmental contaminants in marine 

mammals. In: Howard, E. B. (ed.), Pathobiology of Marine Mammal Diseases. CRC Press, Boca 

Raton, Florida. 

Carretta, J. V., K. A. Forney and J. L. Laake. 1998. The abundance of southern California coastal 

bottlenose dolphins estimated from tandem aerial surveys. Mar. Mamm. Sci. 14:655-675. 

Defran, R. H. and D. W. Weller. 1999. Occurrence, distribution, site fidelity and school size of bottlenose 

dolphins (Tursiops truncatus) off San Diego, California. Mar. Mamm. Sci. 15:366-380. 

99
Defran, R. H., D. W. Weller, D. L. Kelly, and M. A. Espinosa. 1999. Range characteristics of Pacific 

coast bottlenose dolphins (Tursiops truncatus) in the Southern California Bight. Mar. Mamm. Sci. 

15:381-393. 

Dudzik, K.J. 1999. Population dynamics of the Pacific coast bottlenose dolphin (Tursiops truncatus). 

M.S. Thesis, San Diego State University, San Diego, California 92182. 63pp. 

Dudzik, K.J., K.M. Baker, and D.W. Weller. 2006. Mark-recapture abundance estimate of California 

coastal stock bottlenose dolphins: February 2004 to April 2005. SWFSC Administrative Report 

LJ-06-02C, available from Southwest Fisheries Science Center, 8604 La Jolla Shores Drive, La 

Jolla, CA 92037. 15p. 

Feinholz, D.M. 1996. Pacific coast bottlenose dolphins (Tursiops truncatus) in Monterey Bay, California. 

M.S. Thesis, San Jose State University, San Jose, CA. 78p.

Forney, K.A., J. Barlow, M.M. Muto, M. Lowry, J. Baker, G. Cameron, J. Mobley, C. Stinchcomb, and 

J.V. Carretta. 2000. U.S. Pacific Marine Mammal Stock Assessments: 2000. U.S. Department of 

Commerce, NOAA Technical Memorandum NMFS-SWFSC-300. 276p. 

Hansen, L. J. 1990. California coastal bottlenose dolphins. In: S. Leatherwood and R.R. Reeves (eds.), 

The Bottlenose Dolphin, p. 403-420. Academic Press, Inc., San Diego. 

Hansen, L. J. and R. H. Defran. 1990. A comparison of photo-identification studies of California coastal 

bottlenose dolphins. Rep. Int. Whal. Commn. Special Issue 12:101-104. 

Hanson, M.T. and R.H. Defran. 1993. The behavior and feeding ecology of the Pacific coast bottlenose 

dolphin, Tursiops truncatus. Aquatic Mammals 19:127-142. 

Julian, F. and M. Beeson. 1998. Estimates of mammal, turtle and bird mortality for two California gillnet 

fisheries: 1990-1995. Fish. Bull. 96:271-284. 

Lipscomb, T. P., F. Y. Schulman, D. Moffett, and S. Kennedy. 1994. Morbilliviral disease in Atlantic 

bottlenose dolphins (Tursiops truncatus) from the 1987-88 epizootic. Journal of Wildlife Diseases 

30:567-571. 

Lowther, J. 2006. Genetic variation of coastal and offshore bottlenose dolphins, Tursiops truncatus, in the 

eastern North Pacific Ocean. M.S. Thesis, University of San Diego, San Diego, California, USA. 

126 p. 

Lowther, J.L., F.I. Archer, and D.W. Weller. Manuscript in preparation. Genetic variation of coastal and 

offshore bottlenose dolphins, Tursiops truncatus, in the eastern North Pacific Ocean. 

O'Shea, T. J., R. L. Brownell, Jr., D. R. Clark, W. A. Walker, M. L. Gray, and T. G. Lamont. 1980. 

Organochlorine pollutants in small cetaceans from the Pacific and South Atlantic Oceans, 

November 1968-June 1976. Pesticides Monitoring Journal 14:35-46. 

O’Shea, T. J., R. R. Reeves, and A. Kirk Long (eds.). 1999. Marine Mammals and Persistent Ocean 

Contaminants: Proceedings of the Marine Mammal Commission Workshop, Keystone, Colorado, 

12-15 October 1998. Marine Mammal Commission, Bethesda, MD. 150pp. 

NMFS, Southwest Fisheries Science Center. P.O. Box 271, La Jolla, CA 92038-0271 

Norris, K. S. and J. H. Prescott. 1961. Observation on Pacific cetaceans of Californian and Mexican 

waters. University of California Publications in Zoology 63:291-402. University of California 

Press, Berkeley and Los Angeles. 

Reeves, R. R. and S. Leatherwood. 1984. Live-capture fisheries for cetaceans in USA and Canadian 

waters, 1973-1982. Rep. Int. Whal. Commn. 34:497-507. 

Ross, G. J. B. and V. G. Cockcroft. 1990. Comments on Australian bottlenose dolphins and the taxonomic 

status of Tursiops aduncus (Ehrenberg, 1832). In: The Bottlenose Dolphin (eds. S. Leatherwood 

and R. R. Reeves). pp. 101-128. Academic Press, 653pp. 

Schafer, H. A., R. W. Gossett, C. F. Ward, and A. M. Westcott. 1984. Chlorinated hydrocarbons in marine 

mammals. Biennial Report, 1983-84, Southern California Coastal Water Research Project, Long 

Beach, California. 

Van Waerebeek, K., J. C. Reyes, A. J. Read, and J. S. McKinnon. 1990. Preliminary observations of 

bottlenose dolphins from the Pacific coast of South America. In: The Bottlenose Dolphin (eds. S. 

Leatherwood and R. R. Reeves). pp. 143-154 Academic Press, 653 pp. 

Walker, W. A. 1975. Review of the live-capture fishery for smaller cetaceans taken in Southern California 

waters for public display, 1966-77. J. Fish. Res. Board. Can. 32:1197-1211. 

Walker, W. A. 1981. Geographical variation in morphology and biology of bottlenose dolphins (Tursiops) 

in the eastern North Pacific. Admin. Rep. LJ-81-03C. Southwest Fisheries Science Center, 

National Marine Fisheries Service, P.O. Box 271, La Jolla, CA 92038, USA. 52p. 

100
Ward, B.G. 1999. Movement patterns and feeding ecology of the Pacific coast bottlenose dolphin 

(Tursiops truncatus). M.S. Thesis, San Diego State University, San Diego, California, 92182. 

98pp. 

Wells, R. S., L. J. Hansen, A. B. Baldridge, T. P. Dohl, D. L. Kelly and R. H Defran. In: S. Leatherwood 

and R. R. Reeves (eds.), The Bottlenose Dolphin, p. 421-431. Academic Press, Inc., San Diego. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the 

GAMMS Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commerce, NOAA Tech. 

Memo. NMFS-OPR-12. 93 pp. 

101
Revised 10/30/2007 

BOTTLENOSE DOLPHIN (Tursiops truncatus): 

California/Oregon/Washington Offshore Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

Bottlenose dolphins are 

distributed world-wide in tropical 

and warm-temperate waters. In 

many regions, including California, 

separate coastal and offshore 

populations are known (Walker 

1981; Ross and Cockcroft 1990; 

Van Waerebeek et al. 1990; 

Lowther 2006; Lowther et al. in 

prep.). On surveys conducted off 

California, offshore bottlenose 

dolphins have been found at 

distances greater than a few 

kilometers from the mainland and 

throughout the Southern California 

Bight. They have also been 

documented in offshore waters as 

far north as about 41o

N (Figure 1), 

and they may range into Oregon and 

Washington waters during warmwater periods. Sighting records off 

California and Baja California (Lee 

1993; Mangels and Gerrodette 

1994) suggest that offshore 

bottlenose dolphins have a 

continuous distribution in these two 

regions. Based on aerial surveys 

conducted during winter/spring 

1991-92 (Forney et al. 1995) and 

shipboard surveys conducted in 

summer/fall 1991 (Barlow 1995), no 

seasonality in distribution is 

apparent (Forney and Barlow 1998). 

Offshore bottlenose dolphins are not 

restricted to U.S. waters, but cooperative 

management agreements with Mexico exist 

only for the tuna purse seine fishery and not 

for other fisheries which may take this 

species (e.g. gillnet fisheries). Therefore, 

the management stock includes only animals found within U.S. waters. For the Marine Mammal Protection 

Act (MMPA) stock assessment reports, bottlenose dolphins within the Pacific U.S. Exclusive Economic 

Zone are divided into three stocks: 1) California coastal stock, 2) California, Oregon and Washington 

offshore stock (this report), and 3) Hawaiian stock. 

OREGON

WASHINGTON

CALIFORNIA

POPULATION SIZE

 The most recent shipboard surveys conducted within 300 nmi of the coasts of California, Oregon, 

and Washington were in and 2001 (Barlow 2003) and 2005 (Forney 2007). Because the distribution of 

bottlenose dolphins appears to vary interannually and they may spend time outside the U.S. Exclusive 

Economic Zone, a multi-year average abundance estimate is the most appropriate for management within 

U.S. waters. The most comprehensive multi-year average abundance is the geometric mean abundance 

Figure 1. Offshore bottlenose dolphin sightings 

based on shipboard surveys off California, 

Oregon, and Washington, 1991-2005 (see 

Appendix 2 for data sources and information on 

timing and location of survey effort). Dashed line 

represents the U.S. EEZ, thin lines indicate 

completed transect effort of all surveys combined. 

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

45°0'0"N

40°0'0"N

102
estimate for California, Oregon and Washington waters based on the 2001-2005 ship surveys, or 3,257 (CV 

= 0.43) offshore bottlenose dolphins (Barlow 2003, Forney 2007). 

Minimum Population Estimate

 The log-normal 20th percentile of the 2001-2005 average abundance estimate is 2,295 offshore 

bottlenose dolphins. 

Current Population Trend

 No information on trends in abundance of offshore bottlenose dolphins is available. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No information on current or maximum net productivity rates is available for this population of 

offshore bottlenose dolphins. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum 

population size (2,295) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times

a recovery factor of 0.50 (for a species of unknown status with fishery mortality rate CV < 0.30; Wade and 

Angliss 1997), resulting in a PBR of 23 offshore bottlenose dolphins per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

 A summary of known fishery mortality and injury for this stock of bottlenose dolphin is shown in 

Table 1. More detailed information on these fisheries is provided in Appendix 1. Mortality estimates for 

the California drift gillnet fishery are included for the five most recent years of monitoring, 2000-2004 

(Carretta and Chivers 2004, Carretta et al. 2005a, 2005b). After the 1997 implementation of a Take 

Reduction Plan, which included skipper education workshops and required the use of pingers and minimum 

6-fathom extenders, overall cetacean entanglement rates in the drift gillnet fishery dropped considerably 

(Barlow and Cameron 2003). However, because of interannual variability in entanglement rates and the 

rarity of bottlenose dolphin entanglements, additional years of data will be required to fully evaluate the 

effectiveness of pingers for reducing mortality of this particular species. In 2004, a bottlenose dolphin 

stranded dead near Newport Beach, California, with its flukes cut off, suggestive of an interaction with an 

entangling net fishery. The haplotype of this animal matched those of known offshore bottlenose dolphins 

(Lowther 2006, Lowther et al., in prep). Mean annual takes in Table 1 are based on 2000-2004 data. This 

results in an average estimate of 0.2 offshore bottlenose dolphins taken annually. 

Table 1. Summary of available information on the incidental mortality and injury of bottlenose dolphins 

(California/ Oregon/Washington Offshore Stock) in commercial fisheries that might take this species. 

Mean annual takes are based on 2000-2004 data unless noted otherwise. 

Fishery Name Data Type Year(s) 

Percent 

Observer 

Coverage

Observed 

Mortality

Estimated Annual 

Mortality

Mean Annual 

Takes (CV in 

parentheses)

CA/OR thresher 

shark/swordfish drift 

gillnet fishery

observer 

2000 

2001 

2002 

2003 

2004 

22.9% 

20.4% 

22.1% 

20.2% 

20.6% 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0 

Unknown fishery strandings 2004 1 ≥1 ≥0.2 (n/a) 

Minimum total annual takes ≥0.2 (n/a) 

 Drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of Baja 

California, Mexico and may take animals from this population. Quantitative data are available only for the 

Mexican swordfish drift gillnet fishery, which uses vessels, gear, and operational procedures similar to 

those in the U.S. drift gillnet fishery, although nets may be up to 4.5 km long (Holts and Sosa-Nishizaki 

1998). The fleet increased from two vessels in 1986 to 31 vessels in 1993 (Holts and Sosa-Nishizaki 1998). 

The total number of sets in this fishery in 1992 can be estimated from data provided by these authors to be 

103
approximately 2700, with an observed rate of marine mammal bycatch of 0.13 animals per set (10 marine 

mammals in 77 observed sets; Sosa-Nishizaki et al. 1993). This overall mortality rate is similar to that 

observed in California driftnet fisheries during 1990-95 (0.14 marine mammals per set; Julian and Beeson, 

1998), but species-specific information is not available for the Mexican fisheries. Previous efforts to 

convert the Mexican swordfish driftnet fishery to a longline fishery have resulted in a mixed-fishery, with 

20 vessels alternately using longlines or driftnets, 23 using driftnets only, 22 using longlines only, and 

seven with unknown gear type (Berdegué 2002). 

 Offshore bottlenose dolphins are often associated with Risso's dolphins and pilot whales, for 

which mortality has been documented in the squid purse seine fishery off Southern California (Heyning et 

al. 1994). Based on this association, offshore bottlenose dolphins may also have experienced some 

mortality in this fishery. However these would probably represent animals killed intentionally to protect 

catch or gear, rather than incidental kills, and such intentional takes are now illegal under the 1994 

Amendment to the MMPA. 

 

Other removals

 Twenty-seven bottlenose dolphins were captured off California between 1966 and 1982 (Walker 

1975; Reeves and Leatherwood 1984). Based on the locations of capture activities, these animals probably 

were offshore bottlenose dolphins (Walker 1975). No additional captures of bottlenose dolphins off 

California have been documented since 1982, and no MMPA live-capture permits are currently active for 

this species. 

STATUS OF STOCK

 The status of offshore bottlenose dolphins in California relative to OSP is not known, and there are 

insufficient data to evaluate trends in abundance. No habitat issues are known to be of concern for this 

species. They are not listed as "threatened" or "endangered" under the Endangered Species Act nor as 

"depleted" under the MMPA. Because average annual fishery takes (0.2/year) are less than the calculated 

PBR (23), offshore bottlenose dolphins are not classified as a "strategic" stock under the MMPA. The total 

fishery mortality and serious injury for this stock is less than 10% of the PBR and thus can be considered 

to be insignificant and approaching zero. 

REFERENCES

Barlow, J. 1995. The abundance of cetaceans in California waters. Part I: Ship surveys in summer and fall 

of 1991. Fish. Bull. 93:1-14. 

Barlow, J. 1997. Preliminary estimates of cetacean abundance off California, Oregon and Washington 

based on a 1996 ship survey and comparisons of passing and closing modes. Admin. Rep. LJ-97-

11, Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 25p. 

Barlow, J. and G. A. Cameron. 2003. Field experiments show that acoustic pingers reduce marine mammal 

bycatch in the California drift gillnet fishery. Marine Mammal Science 19(2):265-283. 

Barlow, J., K. A. Forney, P. S. Hill, R. L. Brownell, Jr., J. V. Carretta, D. P. DeMaster, F. Julian, M. S. 

Lowry, T. Ragen, and R. R. Reeves. 1997. U.S. Pacific Marine Mammal Stock Assessments: 

1996. U.S. Dep. Commer., NOAA Tech. Memo. NMFS-SWFSC-248. 223p. 

Barlow, J. and T. Gerrodette. 1996. Abundance of cetaceans in California waters based on 1991 and 1993 

ship surveys. U.S. Dep. Commer., NOAA Tech. Memo. NMFS-SWFSC-233. 15 pp. 

Barlow, J. 2003. Preliminary estimates of the abundance of cetaceans along the U.S. west coast: 

1991_2001. Southwest Fisheries Science Center Administrative Report LJ_03_03. Available 

from SWFSC, 8604 La Jolla Shores Dr., La Jolla CA 92037. 31p. 

Berdegué, J. 2002. Depredación de las especies pelágicas reservadas a la pesca deportiva y especies en 

peligro de extinción con uso indiscriminado de artes de pesca no selectivas (palangres, FAD's, 

trampas para peces y redes de agallar fijas y a la deriva) por la flota palangrera Mexicana. 

Fundación para la conservación de los picudos. A.C. Mazatlán, Sinaloa, 21 de septiembre. 

Carretta, J.V. and S.J. Chivers. 2004. Preliminary estimates of marine mammal mortality and biological 

sampling of cetaceans in California gillnet fisheries for 2003. Paper SC/56/SM1 presented to the 

IWC Scientific Committee, June 2004 (unpublished). [Available from Southwest Fisheries 

Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 

92037, USA]. 

104
Carretta, J.V., S.J. Chivers, and K. Danil. 2005a. Preliminary estimates of marine mammal bycatch, 

mortality, and biological sampling of cetaceans in California gillnet fisheries for 2004. 

Administrative Report LJ-05-10, available from Southwest Fisheries Science Center, 8604 La 

Jolla Shores Drive, La Jolla, California, 92037. 17 p. 

Carretta, J.V., T. Price, D. Petersen, and R. Read. 2005b. Estimates of marine mammal, sea turtle, and 

seabird mortality in the California drift gillnet fishery for swordfish and thresher shark, 1996-

2002. Marine Fisheries Review 66(2):21-30.Forney, K. A. and J. Barlow. 1998. Seasonal 

patterns in the abundance and distribution of California cetaceans, 1991-92. Mar. Mamm. Sci. 

14:460-489. 

Forney, K. A., J. Barlow and J. V. Carretta. 1995. The abundance of cetaceans in California waters. Part 

II: Aerial surveys in winter and spring of 1991 and 1992. Fish. Bull. 93:15-26. 

Forney, K.A. 2007. Preliminary estimates of cetacean abundance along the U.S. west coast and within 

four National Marine Sanctuaries during 2005. U.S. Department of Commerce, NOAA Technical 

Memorandum NMFS-SWFSC-406. 27 p. 

Heyning, J. E., T. D. Lewis and C. D. Woodhouse. 1994. A note on odontocete mortality from fishing 

gear entanglements off Southern California. Rep. Int. Whal. Commn. Special Issue 15:439-442. 

Holts, D. and O. Sosa-Nishizaki. 1998. Swordfish, Xiphias gladius, fisheries of the eastern North Pacific 

Ocean. In: I. Barrett, O. Sosa-Nishizaki and N. Bartoo (eds.). Biology and fisheries of swordfish, 

Xiphias gladius. Papers from the International Symposium on Pacific Swordfish, Ensenada 

Mexico, 11-14 December 1994. U.S. Dep. Commer., NOAA Tech. Rep. NMFS 142, 276 p. 

Julian, F. 1997. Cetacean mortality in California gill net fisheries: Preliminary estimates for 1996. Paper 

SC/49/SM02 presented to the International Whaling Commission, September 1997 (unpublished). 

13 pp. 

Julian, F. and M. Beeson. 1998. Estimates of mammal, turtle and bird mortality for two California gillnet 

fisheries: 1990-1995. Fish. Bull. 96:271-284. 

Lee, T. 1993. Summary of cetacean survey data collected between the years of 1974 and 1985. U.S. Dep. 

Commer., NOAA Tech. Memo. NMFS-SWFSC-181. 184 pp. 

Lowther, J. 2006. Genetic variation of coastal and offshore bottlenose dolphins, Tursiops truncatus, in the 

eastern North Pacific Ocean. M.S. Thesis, University of San Diego, San Diego, California, USA. 

126 p. 

Lowther, J.L., F.I. Archer, and D.W. Weller. Manuscript in preparation. Genetic variation of coastal and 

offshore bottlenose dolphins, Tursiops truncatus, in the eastern North Pacific Ocean. 

Mangels, K. F. and Gerrodette, T. 1994. Report of cetacean sightings during a marine mammal survey in 

the eastern Pacific Ocean and Gulf of California aboard the NOAA ships McARTHUR and DAVID 

STARR JORDAN July 28 - November 6, 1993. NOAA Tech. Memo. NMFS, NMFS-SWFSC-211. 

88 pp. 

Reeves, R. R. and S. Leatherwood. 1984. Live-capture fisheries for cetaceans in USA and Canadian 

waters, 1973-1982. Rep. Int. Whal. Commn 34:497-507. 

Ross, G. J. B. and V. G. Cockcroft. 1990. Comments on Australian bottlenose dolphins and the taxonomic 

status of Tursiops aduncus (Ehrenberg, 1832). In: The Bottlenose Dolphin (eds. S. Leatherwood 

and R. R. Reeves). pp. 101-128. Academic Press, 653pp. 

Sosa-Nishizaki, O., R. De la Rosa Pacheco, R. Castro Longoria, M. Grijalva Chon, and J. De la Rosa 

Velez. 1993. Estudio biologico pesquero del pez (Xiphias gladius) y otras especies de picudos 

(marlins y pez vela). Rep. Int. CICESE, CTECT9306. 

Van Waerebeek, K., J. C. Reyes, A. J. Read, and J. S. McKinnon. 1990. Preliminary observations of 

bottlenose dolphins from the Pacific coast of South America. In: The Bottlenose Dolphin (eds. S. 

Leatherwood and R. R. Reeves). pp. 143-154 Academic Press, 653 pp. 

Walker, W. A. 1975. Review of the live-capture fishery for smaller cetaceans taken in Southern California 

waters for public display, 1966-77. J. Fish. Res. Board. Can. 32:1197-1211. 

Walker, W. A. 1981. Geographical variation in morphology and biology of bottlenose dolphins (Tursiops) 

in the eastern North Pacific. Admin. Rep. LJ-81-03C. Southwest Fisheries Science Center, 

National Marine Fisheries Service, La Jolla, CA 92038. 52p. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the 

GAMMS Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. 

Memo. NMFS-OPR-12. 93 pp. 

105
Revised 10/30/2007 

STRIPED DOLPHIN (Stenella coeruleoalba): 

California/Oregon/Washington Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

 Striped dolphins are 

distributed world-wide in tropical 

and warm-temperate pelagic waters. 

On recent shipboard surveys 

extending about 300 nmi offshore of 

California, they were sighted within 

about 100-300 nmi from the coast 

(Figure 1). No sightings have been 

reported for Oregon and 

Washington waters, but striped 

dolphins have stranded in both 

states (Oregon Department of Fish 

and Wildlife, unpublished data; 

Washington Department of Fish and 

Wildlife, unpublished data). Striped 

dolphins are also commonly found 

in the central North Pacific, but 

sampling between this region and 

California has been insufficient to 

determine whether the distribution 

is continuous. Based on sighting 

records off California and Mexico, 

striped dolphins appear to have a 

continuous distribution in offshore 

waters of these two regions (Perrin 

et al. 1985; Mangels and Gerrodette 

1994). No information on possible 

seasonality in distribution is 

available, because the California 

surveys which extended 300 nmi 

offshore were conducted only 

during the summer/fall period. 

Although striped dolphins are not restricted 

to U.S. waters, cooperative management 

agreements with Mexico exist only for the 

tuna purse seine fishery and not for other 

fisheries which may take this species (e.g. 

gillnet fisheries). Therefore, the 

management stock includes only animals 

found within U.S. waters. For the Marine Mammal Protection Act (MMPA) stock assessment reports, 

striped dolphins within the Pacific U.S. Exclusive Economic Zone are divided into two discrete, noncontiguous areas: 1) waters off California, Oregon and Washington (this report), and 2) waters around 

Hawaii. 

OREGON

WASHINGTON

CALIFORNIA

POPULATION SIZE

 Abundance is estimated from two summer/fall shipboard surveys conducted within 300 nmi of 

the coasts of California, Oregon and Washington in 2001 (Barlow 2003) and 2005 (Forney 2007). The 

abundance of striped dolphins in this region appears to be variable between years and may be affected by 

oceanographic conditions, as with other odontocete species (Forney 1997, Forney and Barlow 1998). 

Because animals may spend time outside the U.S. Exclusive Economic Zone as oceanographic conditions 

Figure 1. Striped dolphin sightings based on 

aerial and shipboard surveys off California, 

Oregon, and Washington, 1991-2005 (see 

Appendix 2 for data sources and information on 

timing and location of survey effort). Dashed line 

represents the U.S. EEZ, thin lines indicate the 

completed transect effort of all surveys combined. 

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

45°0'0"N

40°0'0"N

106
change, a multi-year average abundance estimate is the most appropriate for management within U.S. 

waters. The 2001-2005 geometric mean abundance estimate for California, Oregon and Washington waters 

based on the 2001 and 2005 ship surveys is 23,883 (CV = 0.44) striped dolphins (Barlow 2003, Forney 

2007). 

Minimum Population Estimate

 The log-normal 20th percentile of the 2001-2005 mean abundance estimate is 16,737 striped 

dolphins. 

Current Population Trend

 Prior to a 1991 shipboard survey (Barlow 1995), striped dolphins were not thought to be common 

off California (Leatherwood et al. 1982), and two surveys extending approximately 200 nmi offshore of 

California and Baja California in 1979 and 1980 resulted in only one sighting of three striped dolphins 

(Smith et al. 1986). Thus it is possible that striped dolphin abundance off California has increased over the 

last decade (consistent with the observed warming trend for these waters; Roemmich 1992); however, no 

definitive statement can be made, because statistical estimates of abundance were not obtained for the 

earlier surveys. Estimates of abundance from surveys conducted in 1991/93, 1996, 2001, and 2005 in 

California waters were 28,396 (CV = 0.31); 5,489 (0.48); 22,316 (0.65); and 23,883 (0.44) striped dolphin, 

respectively (Barlow 2003; Forney 2007). Currently, there is no evidence of a trend in abundance for this 

stock. 

 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No information on current or maximum net productivity rates is available for striped dolphins off 

California. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum 

population size (16,737) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times

a recovery factor of 0.50 (for a species of unknown status with no known fishery mortality; Wade and 

Angliss 1997), resulting in a PBR of 167 striped dolphins per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

 A summary of recent fishery mortality and injury for this stock of striped dolphin is shown in 

Table 1. More detailed information on these fisheries is provided in Appendix 1. Mortality estimates for 

the California set and drift gillnet fisheries are included in Table 1 for the five most recent years of 

monitoring, 2000-2004 (Carretta and Chivers 2004, Carretta et al. 2005a, 2005b). No striped dolphins were 

observed killed in the most recent five-year period. One striped dolphin was observed killed in the drift 

gillnet fishery in 1994. After the 1997 implementation of a Take Reduction Plan, which included skipper 

education workshops and required the use of pingers and minimum 6-fathom extenders, overall cetacean 

entanglement rates in the drift gillnet fishery dropped considerably (Barlow and Cameron 2003). However, 

because of interannual variability in entanglement rates and the rarity of striped dolphin entanglements, 

additional years of data will be required to fully evaluate the effectiveness of pingers for reducing mortality 

of this particular species. Mean annual takes in Table 1 are based on 2000-2004 data. This results in an 

average estimate of zero striped dolphins taken annually. 

 Drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of Baja 

California, Mexico and may take animals from this population. Quantitative data are available only for the 

Mexican swordfish drift gillnet fishery, which uses vessels, gear, and operational procedures similar to 

those in the U.S. drift gillnet fishery, although nets may be up to 4.5 km long (Holts and Sosa-Nishizaki 

1998). The fleet increased from two vessels in 1986 to 31 vessels in 1993 (Holts and Sosa-Nishizaki 1998). 

The total number of sets in this fishery in 1992 can be estimated from data provided by these authors to be 

approximately 2700, with an observed rate of marine mammal bycatch of 0.13 animals per set (10 marine 

mammals in 77 observed sets; Sosa-Nishizaki et al. 1993). This overall mortality rate is similar to that 

observed in California driftnet fisheries during 1990-95 (0.14 marine mammals per set; Julian and Beeson, 

1998), but species-specific information is not available for the Mexican fisheries. Previous efforts to 

convert the Mexican swordfish driftnet fishery to a longline fishery have resulted in a mixed-fishery, with 

107
20 vessels alternately using longlines or driftnets, 23 using driftnets only, 22 using longlines only, and 

seven with unknown gear type (Berdegué 2002). 

Table 1. Summary of available information on the incidental mortality and injury of striped dolphins 

(California/ Oregon/Washington Stock) in commercial fisheries that might take this species. Coefficients 

of variation for mortality estimates are provided in parentheses. Mean annual takes are based on 2000-

2004 data unless noted otherwise. 

Fishery Name Data Type

Year(s) 

Percent 

Observer

Coverage

Observed

Mortality

Estimated Annual 

Mortality

Mean 

Annual Takes 

(CV in 

parentheses)

CA/OR thresher 

shark/swordfish drift 

gillnet fishery

observer 2000-2004 20-23% 0 0 0

Minimum total annual takes 0

STATUS OF STOCK

 The status of striped dolphins in California relative to OSP is not known, and there are insufficient 

data to evaluate potential trends in abundance. No habitat issues are known to be of concern for this 

species. They are not listed as "threatened" or "endangered" under the Endangered Species Act nor as 

"depleted" under the MMPA. The average annual human-caused mortality in 2000-2004 is zero. Because 

recent mortality is zero, striped dolphins are not classified as a "strategic" stock under the MMPA, and the 

total fishery mortality and serious injury for this stock can be considered to be insignificant and 

approaching zero. 

REFERENCES

Barlow, J. 1995. The abundance of cetaceans in California waters. Part I: Ship surveys in summer and fall 

of 1991. Fish. Bull. 93:1-14. 

Barlow, J. 1997. Preliminary estimates of cetacean abundance off California, Oregon and Washington 

based on a 1996 ship survey and comparisons of passing and closing modes. Admin. Rep. LJ-97-

11. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 25p. 

Barlow, J. and G. A. Cameron. 2003. Field experiments show that acoustic pingers reduce marine mammal 

bycatch in the California drift gillnet fishery. Marine Mammal Science 19(2):265-283. 

Barlow, J. and T. Gerrodette. 1996. Abundance of cetaceans in California waters based on 1991 and 1993 

ship surveys. U.S. Dep. Commer., NOAA Tech. Memo. NMFS-SWFSC-233. 15 pp. 

Barlow, J. 2003. Preliminary estimates of the abundance of cetaceans along the U.S. west coast: 

1991_2001. Southwest Fisheries Science Center Administrative Report LJ_03_03. Available 

from SWFSC, 8604 La Jolla Shores Dr., La Jolla CA 92037. 31p. 

Berdegué, J. 2002. Depredación de las especies pelágicas reservadas a la pesca deportiva y especies en 

peligro de extinción con uso indiscriminado de artes de pesca no selectivas (palangres, FAD's, 

trampas para peces y redes de agallar fijas y a la deriva) por la flota palangrera Mexicana. 

Fundación para la conservación de los picudos. A.C. Mazatlán, Sinaloa, 21 de septiembre. 

Carretta, J.V. and S.J. Chivers. 2004. Preliminary estimates of marine mammal mortality and biological 

sampling of cetaceans in California gillnet fisheries for 2003. Paper SC/56/SM1 presented to the 

IWC Scientific Committee, June 2004 (unpublished). [Available from Southwest Fisheries 

Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 

92037, USA]. 

Carretta, J.V., S.J. Chivers, and K. Danil. 2005a. Preliminary estimates of marine mammal bycatch, 

mortality, and biological sampling of cetaceans in California gillnet fisheries for 2004. 

Administrative Report LJ-05-10, available from Southwest Fisheries Science Center, 8604 La 

Jolla Shores Drive, La Jolla, California, 92037. 17 p. 

Carretta, J.V., T. Price, D. Petersen, and R. Read. 2005b. Estimates of marine mammal, sea turtle, and 

seabird mortality in the California drift gillnet fishery for swordfish and thresher shark, 1996-

2002. Marine Fisheries Review 66(2):21-30. 

108
Forney, K. A. 1997. Patterns of variability and environmental models of relative abundance for California 

cetaceans. Ph.D. dissertation, Scripps Institution of Oceanography, University of California, San 

Diego. 

Forney, K. A. and J. Barlow. 1998. Seasonal patterns in the abundance and distribution of California 

cetaceans, 1991-92. Mar. Mamm. Sci. 14:460-489. 

Forney, K.A. 2007. Preliminary estimates of cetacean abundance along the U.S. west coast and within 

four National Marine Sanctuaries during 2005. U.S. Department of Commerce, NOAA Technical 

Memorandum NMFS-SWFSC-406. 27p. 

Holts, D. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La Jolla, 

CA 92038. 

Holts, D. and O. Sosa-Nishizaki. 1998. Swordfish, Xiphias gladius, fisheries of the eastern North Pacific 

Ocean. In: I. Barrett, O. Sosa-Nishizaki and N. Bartoo (eds.). Biology and fisheries of swordfish, 

Xiphias gladius. Papers from the International Symposium on Pacific Swordfish, Ensenada 

Mexico, 11-14 December 1994. U.S. Dep. Commer., NOAA Tech. Rep. NMFS 142, 276 p. 

Julian, F. and M. Beeson. 1998. Estimates of mammal, turtle and bird mortality for two California gillnet 

fisheries: 1990-1995. Fish. Bull. 96:271-284. 

Leatherwood, S., R. R. Reeves, W. F. Perrin, and W. E. Evans. 1982. Whales, dolphins and porpoises of 

the eastern North Pacific and adjacent Arctic waters. A guide to their identification. NOAA Tech. 

Rep. NMFS Circular 444, U.S. Dep. Commer., NOAA, NMFS. 245 pp. 

Mangels, K. F. and Gerrodette, T. 1994. Report of cetacean sightings during a marine mammal survey in 

the eastern Pacific Ocean and Gulf of California aboard the NOAA ships McARTHUR and DAVID 

STARR JORDAN July 28 - November 6, 1993. U.S. Dep. Commer., NOAA Tech. Memo. NMFSSWFSC-211. 88 pp. 

Perrin, W. F., M. D. Scott, G. J. Walker and V. L. Cass. 1985. Review of geographical stocks of tropical 

dolphins (Stenella spp. and Delphinus delphis) in the eastern Pacific. NOAA Tech. Rep. NMFS 

28. Available from NMFS, Southwest Fisheries Science Center, P.O. Box 271, La Jolla, 

California, 92038. 28p. 

Roemmich, D. 1992. Ocean warming and sea level rise along the southwest U.S. coast. Science 257:373-

375. 

Smith, R. C., P. Dustan, D. Au, K. S. Baker, and E. A. Dunlap. 1986. Distribution of cetaceans and seasurface chlorophyll concentrations in the California Current. Marine Biology 91:385-402. 

Sosa-Nishizaki, O., R. De la Rosa Pacheco, R. Castro Longoria, M. Grijalva Chon, and J. De la Rosa 

Velez. 1993. Estudio biologico pesquero del pez (Xiphias gladius) y otras especies de picudos 

(marlins y pez vela). Rep. Int. CICESE, CTECT9306. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the 

GAMMS Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. 

Memo. NMFS-OPR-12. 93 pp. 

109
Revised 10/30/2007

SHORT-BEAKED COMMON DOLPHIN (Delphinus delphis): 

California/Oregon/Washington Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

 Short-beaked common 

dolphins are the most abundant 

cetacean off California, and are 

widely distributed between the coast 

and at least 300 nmi distance from 

shore. The abundance of this 

species off California has been 

shown to change on both seasonal 

and inter-annual time scales (Dohl 

et al. 1986; Barlow 1995; Forney et 

al. 1995). Historically, they were 

reported primarily south of Pt. 

Conception (Dohl et al. 1986), but 

have been commonly sighted as far 

north as 42o

N during 1991-2005 

NMFS line-transect vessel surveys 

(Figure 1). Four strandings of 

common dolphins (Delphinus sp.) 

have been reported in Oregon and 

Washington since 1942 (B. 

Norberg, pers. comm.), but three of 

these could not be identified to 

species. One animal, which 

stranded in 1983, was identified as a 

short-beaked common dolphin (J. 

Hodder, pers. comm.). Significant 

seasonal shifts in the abundance and 

distribution of common dolphins 

have been identified based on 

winter/spring 1991-92 and 

summer/fall 1991 surveys (Forney 

and Barlow 1998). Their 

distribution is continuous southward 

into Mexican waters to about 13o

N 

(Perrin et al. 1985; Wade and 

Gerrodette 1993; Mangels and 

Gerrodette 1994), and short-beaked 

common dolphins off California may be 

an extension of the "northern common 

dolphin" stock defined for management 

of eastern tropical Pacific tuna fisheries (Perrin et al. 1985). However, preliminary data on variation in 

dorsal fin color patterns suggest there may be multiple stocks in this region, including at least two possible 

stocks in California (Farley 1995). The less abundant long-beaked common dolphin has only recently been 

recognized as a different species (Heyning and Perrin 1994; Rosel et al. 1994), and much of the available 

information has not differentiated between the two types of common dolphin. Although short-beaked 

common dolphins are not restricted to U.S. waters, cooperative management agreements with Mexico exist 

only for the tuna purse seine fishery and not for other fisheries which may take this species (e.g. gillnet 

fisheries). Under the Marine Mammal Protection Act (MMPA), short-beaked common dolphins involved 

in tuna purse seine fisheries in international waters of the eastern tropical Pacific are managed separately, 

and they are not included in the assessment reports. For the MMPA stock assessment reports, there is a 

OREGON

WASHINGTON

CALIFORNIA

Figure 1. Short-beaked common dolphin sightings 

based on shipboard surveys off California, Oregon, and 

Washington, 1991- 2005 (see Appendix 2, for data 

sources and information on timing and location of 

survey effort). No Delphinus sightings have been made 

off Washington. Dashed line represents the U.S. EEZ, 

thin lines indicate completed transect effort of all 

surveys combined. 

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

45°0'0"N

40°0'0"N

110
single Pacific management stock including only animals found within the U.S. Exclusive Economic Zone 

of California, Oregon and Washington. 

POPULATION SIZE

 The most recent estimates of abundance estimates are based on two summer/fall shipboard 

surveys that were conducted within 300 nmi of the coasts of California, Oregon and Washington in 2001 

(Barlow 2003) and 2005 (Forney 2007). The distribution of short-beaked common dolphins throughout 

this region is highly variable, apparently in response to oceanographic changes on both seasonal and 

interannual time scales (Heyning and Perrin 1994; Forney 1997; Forney and Barlow 1998). As 

oceanographic conditions vary, short-beaked common dolphins may spend time outside the U.S. Exclusive 

Economic Zone, and therefore a multi-year average abundance estimate is the most appropriate for 

management within U.S. waters. The 2001-2005 geometric mean abundance estimate for California, 

Oregon and Washington waters based on the two ship surveys is 487,622 (CV=0.26) short-beaked common 

dolphins (Forney 2007). 

Minimum Population Estimate

 The log-normal 20th percentile of the 2001-2005 abundance estimate is 392,687 short-beaked 

common dolphins. 

Current Population Trend

 In the past, common dolphin abundance has been shown to increase off California during the 

warm-water months (Dohl et al. 1986). Surveys conducted during both cold-water and warm-water 

conditions in 1991 and 1992 (Barlow 1995, Forney et al. 1995) resulted in overall abundance estimates (for 

both types of common dolphins combined) which were considerably greater than historical estimates (Dohl 

et al. 1986). The recent combined abundance estimate for the 2001-2005 summer/fall surveys ( Forney 

2007) is the most precise to date. Environmental models (Forney 1997) and seasonal comparisons (Forney 

and Barlow 1998) have shown that the abundance of short-beaked common dolphins off California varies 

with seasonal and interannual changes in oceanographic conditions. An ongoing decline in the abundance 

of ‘northern common dolphins’ (including both long-beaked and short-beaked common dolphins) in the 

eastern tropical Pacific and along the Pacific coast of Mexico suggests a possible northward shift in the 

distribution of common dolphins (IATTC 1997) during this period of gradual warming of the waters off 

California (Roemmich 1992). The majority of this shift would likely be reflected in an increase in shortbeaked common dolphin abundance. Heyning and Perrin (1994) have detected changes in the proportion of 

short-beaked to long-beaked common dolphins stranding along the California coast, with short-beaked 

common dolphin stranding more frequently prior to the 1982-83 El Niño (which increased water 

temperatures off California), and the long-beaked common dolphin more commonly observed for several 

years afterwards. Thus, it appears that both relative and absolute abundances of these species off California 

may change with varying oceanographic conditions. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 There are no estimates of current or maximum net productivity rates for short-beaked common 

dolphins. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum 

population size (392,687) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) 

times a recovery factor of 0.50 (for a species of unknown status with a mortality rate CV< 0.30; Wade and 

Angliss 1997), resulting in a PBR of 3,927 short-beaked common dolphins per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

A summary of recent fishery mortality and injury for short-beaked common dolphins is shown in 

Table 1. More detailed information on these fisheries is provided in Appendix 1. Mortality estimates for 

the California drift gillnet fishery are included for the five most recent years of monitoring, 2000-2004 

(Carretta and Chivers 2004, Carretta et al. 2005a, 2005b). After the 1997 implementation of a Take 

Reduction Plan, which included skipper education workshops and required the use of pingers and minimum 

111
6-fathom extenders, common dolphin entanglement rates in the drift gillnet fishery dropped considerably 

(Barlow and Cameron 2003) Since the initial pinger experiments, short-beaked common dolphin 

entanglement rates have remained below pre-pinger levels, even though a time/area closure in 2001 shifted 

fishing effort south of Point Conception, California, where common dolphin densities are highest. 

Between 1990-2005, in the region south of Point Conception, there have been 112 short-beaked common 

dolphins entangled in 2,700 sets (4.1 per 100 sets), whereas there were 114 entanglements in 1,946 sets 

without pingers (5.8 per 100 sets) (NMFS, unpublished data). Mean annual takes in Table 1 are based on 

2000-2004 data. This results in an average estimate of 59 (CV = 0.15) short-beaked common dolphins 

taken annually. 

0

0.02

0.04

0.06

0.08

0.1

0.12

1990

1991

1992

1993

1994

1995

1996

1997

1998

1999

2000

2001

2002

2003

2004

2005

Year

Kill/Day

No pingers Pingers

Figure 2. Kill rates of short-beaked common dolphin per set fished in the California drift gillnet fishery for 

swordfish and thresher shark, 1990-2005. Kill rates include observations from pingered and unpingered 

sets. Pingers were not used from 1990-95 and were used experimentally in 1996 and 1997. In 1996, no 

short-beaked common dolphin were observed killed in 146 pingered sets. For the period 1998-2005, more 

than 99% of all observed sets utilized pingers. 

Additional common dolphin mortality has been reported for set gillnets in California (Julian and 

Beeson 1998); however, because of a 1994 ban on gillnets in nearshore areas of Southern California, the 

size of this fishery decreased by about a factor of two (see Appendix 1), and the observer program was 

discontinued. Approximately 4% and 1.8% of the entire fishery was observed in Monterey Bay in 1999 

and 2000, respectively, and no common dolphin were observed taken. Marine Mammal Authorization 

Permit (MMAP) fisher self-reports for 2000-2004 indicate that at least one common dolphin (type not 

specified) was killed. Although these reports are considered unreliable (see Appendix 4 of Hill and 

DeMaster 1998) they represent a minimum mortality for this fishery. 

 Six common dolphin (four not specified) stranded with evidence of fishery interaction (NMFS, 

Southwest Region, unpublished data) between 2000-2004. It is not known which fisheries were 

responsible for these deaths.

 Drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of Baja 

California, Mexico and may take animals from this population. Quantitative data are available only for the 

Mexican swordfish drift gillnet fishery, which uses vessels, gear, and operational procedures similar to 

those in the U.S. drift gillnet fishery, although nets may be up to 4.5 km long (Holts and Sosa-Nishizaki 

1998). The fleet increased from two vessels in 1986 to 31 vessels in 1993 (Holts and Sosa-Nishizaki 1998). 

The total number of sets in this fishery in 1992 can be estimated from data provided by these authors to be 

approximately 2700, with an observed rate of marine mammal bycatch of 0.13 animals per set (10 marine 

mammals in 77 observed sets; Sosa-Nishizaki et al. 1993). This overall mortality rate is similar to that 

observed in California driftnet fisheries during 1990-95 (0.14 marine mammals per set; Julian and Beeson, 

1998), but species-specific information is not available for the Mexican fisheries. Previous efforts to 

convert the Mexican swordfish driftnet fishery to a longline fishery have resulted in a mixed-fishery, with 

112
20 vessels alternately using longlines or driftnets, 23 using driftnets only, 22 using longlines only, and 

seven with unknown gear type (Berdegué 2002). 

Table 1. Summary of available information on the incidental mortality and injury of short-beaked common 

dolphins (California/Oregon/Washington Stock), in commercial fisheries that might take this species. All 

entanglements resulted in the death of the animal. Coefficients of variation for mortality estimates are 

provided in parentheses; n/a = not available. Mean annual takes are based on 2000-2004 data unless noted 

otherwise. 

Fishery Name Data Type Year 

Percent 

Observer 

Coverage

Observed 

Mortality

Estimated Annual 

Mortality

Mean 

Annual Takes 

(CV in 

parentheses)

CA/OR thresher 

shark/swordfish drift 

gillnet fishery

observer 

data 

2000 

2001 

2002 

2003 

2004 

22.9% 

20.4% 

22.1% 

20.2% 

20.6% 

24 

7 

7 

17 

7 

 105 (0.26) 

34 (0.41) 

32 (0.46) 

84 (0.24) 

34 (0.49) 

58 (0.15) 

Common dolphins, species not determined 

CA angel shark/ 

halibut and other 

species large mesh 

(>3.5in) set gillnet 

fishery1

MMAP 

self-reporting 

2000 

2001 

2002 

2003 

2004 

- 

- 

- 

- 

- 

- 

0 

0 

0 

0 

1 

0 

0 

0 

0 

1 

≥0.2 (n/a) 

Unknown fishery strandings 2000-

2004 

 4 unidentified common and 2 short-beaked common 

dolphin stranded with evidence of fishery interations ≥ 1.2 (n/a) 

Minimum total annual takes 59 (0.15) 

1

The set gillnet fishery was observed from 1991-94 and then only in Monterey Bay during 1999-2000, where 20-25% of the local 

fishery was observed. There are no estimates of common dolphin mortality in this fishery because of a lack of recent observer effort. 

Other Mortality

 In the eastern tropical Pacific, 'northern common dolphins' have been incidentally killed in 

international tuna purse seine fisheries since the late 1950's. Cooperative international management 

programs have dramatically reduced overall dolphin mortality in these fisheries during the last decade 

(Joseph 1994). Between 2000-2004, annual fishing mortality of northern common dolphins (potentially 

including both short-beaked and long-beaked common dolphins) ranged between 54 and 159 animals, with 

an average of 102 (IATTC, 2006). Although it is unclear whether these animals are part of the same 

population as short-beaked common dolphins found off California, they are managed separately under a 

section of the MMPA written specifically for the management of dolphins involved in eastern tropical 

Pacific tuna fisheries.

STATUS OF STOCK

 The status of short-beaked common dolphins in Californian waters relative to OSP is not known. 

The observed increase in abundance of this species off California probably reflects a distributional shift 

(Anganuzzi et al. 1993; Barlow 1995; Forney et al. 1995; Forney and Barlow 1998), rather than an overall 

population increase due to growth. No habitat issues are known to be of concern for this species. They are 

not listed as "threatened" or "endangered" under the Endangered Species Act nor as "depleted" under the 

MMPA. The average annual human-caused mortality in 2000-2004 (59 animals) is estimated to be less 

than the PBR (3,927), and therefore they are not classified as a "strategic" stock under the MMPA. The 

total estimated fishery mortality and injury for short-beaked common dolphins is less than 10% of the 

calculated PBR and, therefore, can be considered to be insignificant and approaching zero mortality and 

serious injury rate. 

113
REFERENCES

Anganuzzi, A. A., S. T. Buckland, and K. L Cattanach. 1993. Relative abundance of dolphins associated 

with tuna in the eastern tropical Pacific Ocean: analysis of 1991 data. Rep. Int. Whal. Commn 

43:459-465. 

Barlow, J. 1995. The abundance of cetaceans in California waters. Part I: Ship surveys in summer and fall 

of 1991. Fish. Bull. 93:1-14. 

Barlow, J. 1997. Preliminary estimates of cetacean abundance off California, Oregon and Washington 

based on a 1996 ship survey and comparisons of passing and closing modes. Administrative 

Report LJ-97-11, Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. 

Box 271, La Jolla, CA 92038. 25p. 

Barlow, J. and G. A. Cameron. 2003. Field experiments show that acoustic pingers reduce marine mammal 

bycatch in the California drift gillnet fishery. Marine Mammal Science 19(2):265-283. 

Barlow, J., K. A. Forney, P. S. Hill, R. L. Brownell, Jr., J. V. Carretta, D. P. DeMaster, F. Julian, M. S. 

Lowry, T. Ragen, and R. R. Reeves. 1997. U.S. Pacific Marine Mammal Stock Assessments: 

1996. U.S. Dep. Commer., NOAA Tech. Memo. NMFS-SWFSC-248. 223p. 

Barlow, J. 2003. Preliminary estimates of the abundance of cetaceans along the U.S. west coast: 

1991_2001. Southwest Fisheries Science Center Administrative Report LJ_03_03. Available 

from SWFSC, 8604 La Jolla Shores Dr., La Jolla CA 92037. 31p. 

Berdegué, J. 2002. Depredación de las especies pelágicas reservadas a la pesca deportiva y especies en 

peligro de extinción con uso indiscriminado de artes de pesca no selectivas (palangres, FAD's, 

trampas para peces y redes de agallar fijas y a la deriva) por la flota palangrera Mexicana. 

Fundación para la conservación de los picudos. A.C. Mazatlán, Sinaloa, 21 de septiembre. 

Carretta, J.V. and S.J. Chivers. 2004. Preliminary estimates of marine mammal mortality and biological 

sampling of cetaceans in California gillnet fisheries for 2003. Paper SC/56/SM1 presented to the 

IWC Scientific Committee, June 2004 (unpublished). [Available from Southwest Fisheries 

Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 

92037, USA]. 

Carretta, J.V., S.J. Chivers, and K. Danil. 2005a. Preliminary estimates of marine mammal bycatch, 

mortality, and biological sampling of cetaceans in California gillnet fisheries for 2004. 

Administrative Report LJ-05-10, available from Southwest Fisheries Science Center, 8604 La 

Jolla Shores Drive, La Jolla, California, 92037. 17 p. 

Carretta, J.V., T. Price, D. Petersen, and R. Read. 2005b. Estimates of marine mammal, sea turtle, and 

seabird mortality in the California drift gillnet fishery for swordfish and thresher shark, 1996-

2002. Marine Fisheries Review 66(2):21-30. 

Barlow, J. and T. Gerrodette. 1996. Abundance of cetaceans in California waters based on 1991 and 1993 

ship surveys. NOAA Technical Memorandum NMFS, NOAA-TM-NMFS-SWFSC-233. 

Dohl, T. P., M. L. Bonnell, and R. G. Ford. 1986. Distribution and abundance on common dolphin, 

Delphinus delphis, in the Southern California Bight: A quantitative assessment based upon aerial 

transect data. Fish. Bull. 84:333-343. 

Farley, T. D. 1995. Geographic variation in dorsal fin color of short-beaked common dolphins, Delphinus 

delphis, in the eastern Pacific Ocean. Administrative Report LJ-95-06, Available from National 

Marine Fisheries Service, Southwest Fisheries Science Center, P.O. Box 271, La Jolla, California, 

92038. 

Forney, K. A. 1997. Patterns of variability and environmental models of relative abundance for California 

cetaceans. Ph.D. Dissertation, Scripps Institution of Oceanography, University of California, San 

Diego. 

Forney, K. A. and J. Barlow. 1998. Seasonal patterns in the abundance and distribution of California 

cetaceans, 1991-92. Mar. Mamm. Sci. 14:460-489. 

Forney, K. A., J. Barlow and J. V. Carretta. 1995. The abundance of cetaceans in California waters. Part 

II: Aerial surveys in winter and spring of 1991 and 1992. Fish. Bull. 93:15-26. 

Forney, K.A. 2007. Preliminary estimates of cetacean abundance along the U.S. west coast and within 

four National Marine Sanctuaries during 2005. U.S. Department of Commerce, NOAA Technical 

Memorandum NMFS-SWFSC-406. 27p. 

Heyning, J. E. and W. F. Perrin. 1994. Evidence for two species of common dolphins (Genus Delphinus) 

from the eastern North Pacific. Contr. Nat. Hist. Mus. L.A. County, No. 442. 

114
Hill, P. S. and D. P. DeMaster. 1998. Alaska Marine Mammal Stock Assessments, 1998. U.S. Dep. 

Commer., NOAA Tech. Memo. NMFS-AFSC-97. 166pp. 

Hodder, J. Oregon Institute of Marine Biology, Charleston, OR, 97420. 

Holts, D. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores 

Drive, La Jolla, CA 92037. 

Holts, D. and O. Sosa-Nishizaki. 1998. Swordfish, Xiphias gladius, fisheries of the eastern North Pacific 

Ocean. In: I. Barrett, O. Sosa-Nishizaki and N. Bartoo (eds.). Biology and fisheries of swordfish, 

Xiphias gladius. Papers from the International Symposium on Pacific Swordfish, Ensenada 

Mexico, 11-14 December 1994. U.S. Dep. Commer., NOAA Tech. Rep. NMFS 142, 276 p. 

IATTC. 1997. Annual Report of the Inter-American Tropical Tuna Commission, 1995, La Jolla, 

California. 

IATTC. 2006. Annual Report of the Inter-American Tropical Tuna Commission, 2004, La Jolla, 

California. 96p. 

Joseph, J. 1994. The tuna-dolphin controversy in the eastern Pacific Ocean: biological, economic and 

political impacts. Ocean Dev. Int. Law 25:1-30. 

Julian, F. 1997. Cetacean mortality in California gill net fisheries: Preliminary estimates for 1996. Paper 

SC/49/SM02 presented to the International Whaling Commission, 1997 (unpublished). 13 pp. 

Julian, F. and M. Beeson. 1998. Estimates of mammal, turtle and bird mortality for two California gillnet 

fisheries: 1990-1995. Fish. Bull. 96:271-284. 

Mangels, K. F. and Gerrodette, T. 1994. Report of cetacean sightings during a marine mammal survey in 

the eastern Pacific Ocean and Gulf of California aboard the NOAA ships McARTHUR and DAVID 

STARR JORDAN July 28 - November 6, 1993. NOAA Technical Memorandum NMFS, NOAATM-NMFS-SWFSC-211. 

NMFS, Southwest Fisheries Science Center, P.O. Box 271, La Jolla, CA 92038-027. 

NMFS, Southwest Region, 501 West Ocean Blvd, Long Beach, CA 90802_4213. 

Norberg, B., NMFS, Northwest Region,.7600 Sand Point Way NE, BIN C15700,Seattle, WA 98115_0070. 

Perrin, W. F., M. D. Scott, G. J. Walker and V. L. Cass. Review of geographical stocks of tropical 

dolphins (Stenella spp. and Delphinus delphis) in the eastern Pacific. NOAA Technical Report 

NMFS 28. Available from NMFS, Southwest Fisheries Science Center, P.O. Box 271, La Jolla, 

California, 92038. 28p. 

Roemmich, D. 1992. Ocean warming and sea level rise along the southwest U.S. coast. Science 257:373-

375. 

Rosel, P. E., A. E. Dizon and J. E. Heyning. 1994. Population genetic analysis of two forms of the 

common dolphin (genus Delphinus) utilizing mitochondrial DNA control region sequences. 

Marine Biology 119:159-167. 

Sosa-Nishizaki, O., R. De la Rosa-Pacheco, R. Castro-Longoria, M. Grijalva Chon, and J. De la Rosa 

Velez. 1993. Estudio biologico pesquero del pez (Xiphias gladius) y otras especies de picudos 

(marlins y pez vela). Rep. Int. CICESE, CTECT9306. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the 

GAMMS Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. 

Memo. NMFS-OPR-12. 93 pp. 

Wade, P. R. and T. Gerrodette. 1993. Estimates of cetacean abundance and distribution in the eastern 

tropical Pacific. Rep. Int. Whal. Commn 43:477-493. 

115
Revised 10/30/2007

LONG-BEAKED COMMON DOLPHIN (Delphinus capensis): 

California Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

 Long-beaked common 

dolphins have only recently been 

recognized as a distinct species 

(Heyning and Perrin 1994; Rosel et 

al. 1994). Along the U.S. west 

coast, their distribution overlaps 

with that of the short-beaked 

common dolphin, and much 

historical information has not 

distinguished between these two 

species. Long-beaked common 

dolphins are commonly found 

within about 50 nmi of the coast, 

from Baja California (including the 

Gulf of California) northward to 

about central California (Figure 1). 

Stranding data and sighting records 

indicate that the relative abundance 

of this species off California 

changes both seasonally and interannually, with highest densities 

observed during warm-water events 

(Heyning and Perrin 1994). 

Although long-beaked common 

dolphins are not restricted to U.S. 

waters, cooperative management 

agreements with Mexico exist only 

for the tuna purse seine fishery and 

not for other fisheries which may 

take this species (e.g. gillnet 

fisheries). Under the Marine 

Mammal Protection Act (MMPA), 

long-beaked ("Baja neritic") common 

dolphins involved in eastern tropical 

Pacific tuna fisheries are managed 

separately as part of the 'northern 

common dolphin' stock (Perrin et al. 

1985), and these animals are not 

included in the assessment reports. For the MMPA stock assessment reports, there is a single Pacific 

management stock including only animals found within the U.S. Exclusive Economic Zone of California. 

OREGON

WASHINGTON

CALIFORNIA

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

40°0'0"N

45°0'0"N

Figure 1. Long-beaked common dolphin sightings based on 

shipboard surveys off California, Oregon, and Washington, 

1991-2005 (see Appendix 2 for information on timing and 

location of survey effort). No Delphinus sightings have been 

made off Washington. Dashed line represents the U.S. EEZ, 

thin lines indicate completed transect effort of all surveys 

combined. 

POPULATION SIZE

 Barlow (2003) reported long-beaked common dolphin abundance estimates of 10,799 (CV = 

0.76), 86,414 (CV = 0.74), and 306 (CV = 1.02) for 1991-93, 1996, and 2001 surveys, respectively. The 

most recent abundance estimate is 11,714 (CV = 0.99), based on a 2005 ship line transect survey of 

California, Oregon, and Washington waters (Forney 2007). The distribution and abundance of long-beaked 

common dolphins off California appears to be variable on interannual and seasonal time scales (Heyning 

and Perrin 1994). As oceanographic conditions change, long-beaked common dolphins may move between 

Mexican and U.S. waters, and therefore a multi-year average abundance estimate is the most appropriate 

for management within the U.S. waters. The geometric mean abundance estimate for California, Oregon 

116
and Washington waters based on two ship surveys conducted in 2001 and 2005 is 1,893 (CV=0.65) longbeaked common dolphins (Barlow 2003, Forney 2007). 

Minimum Population Estimate

 The log-normal 20th percentile of the weighted average abundance estimate is 1,152 long-beaked 

common dolphins. 

Current Population Trend

 California waters represent the northern limit for this stock and animals likely move between 

U.S. and Mexican waters. No information on trends in abundance are available for this stock because of 

high interannual variability in line-transect abundance estimates. Heyning and Perrin (1994) detected 

changes in the proportion of short-beaked to long-beaked common dolphins stranding along the California 

coast, with the short-beaked common dolphin stranding more frequently prior to the 1982-83 El Niño 

(which increased water temperatures off California), and the long-beaked common dolphin more 

commonly observed for several years afterwards. Thus, it appears that both relative and absolute 

abundance of these species off California may change with varying oceanographic conditions. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 There are no estimates of current or maximum net productivity rates for long-beaked common 

dolphins. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum 

population size (1,152) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times

a recovery factor of 0.48 (for a species of unknown status with a mortality rate CV >0.30 and <0.60; Wade 

and Angliss 1997), resulting in a PBR of 11 long-beaked common dolphins per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

 A summary of recent fishery mortality and injury for long-beaked common dolphins is shown in 

Table 1. Mean annual takes in Table 1 are based on 2000-2004 data. This results in an average estimate of 

12.5 (CV= 0.70) long-beaked common dolphins taken annually. More detailed information on these 

fisheries is provided in Appendix 1. Mortality estimates for the California drift gillnet fishery are included 

for the five most recent years of monitoring, 2000-2004 ( Carretta and Chivers 2004, Carretta et al. 2005a, 

2005b). After the 1997 implementation of a Take Reduction Plan, which included skipper education 

workshops and required the use of pingers and minimum 6-fathom extenders, common dolphin 

entanglement rates in the drift gillnet fishery dropped considerably (Barlow and Cameron 2003). However, 

because of interannual variability in entanglement rates additional years of data will be required to fully 

evaluate the effectiveness of pingers for reducing mortality of this species in the long term. 

 Additional common dolphin mortality has been reported for set gillnets in California (Julian and 

Beeson 1998); however, because of a 1994 ban on gillnets in nearshore areas of Southern California, the 

size of this fishery decreased by about a factor of two (see Appendix 1), and the observer program was 

discontinued. Approximately 4% and 1.8% of the entire fishery was observed in Monterey Bay in 1999 

and 2000, respectively, and no common dolphin were observed taken. Marine Mammal Authorization 

Permit (MMAP) fisher self-reports for 2000-2004 indicate that at least two common dolphins (type not 

specified) were killed between 2000-2004. Although these reports are considered unreliable (see Appendix 

4 of Hill and DeMaster 1998) they represent a minimum mortality for this fishery. Sixteen common 

dolphins (six unidentified common dolphin and ten long-beaked common dolphin) stranded with evidence 

of fishery interaction (NMFS, Southwest Region, unpublished data) between 2000-2004. Two of the longbeaked common dolphin had portions of ‘halibut’ gillnet around the carcasses and it is not known which 

fisheries were responsible for the remaining mortalities. 

 Drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of Baja 

California, Mexico and may take animals from this population. Quantitative data are available only for the 

Mexican swordfish drift gillnet fishery, which uses vessels, gear, and operational procedures similar to 

those in the U.S. drift gillnet fishery, although nets may be up to 4.5 km long (Holts and Sosa-Nishizaki 

1998). The fleet increased from two vessels in 1986 to 31 vessels in 1993 (Holts and Sosa-Nishizaki 1998). 

117
The total number of sets in this fishery in 1992 can be estimated from data provided by these authors to be 

approximately 2700, with an observed rate of marine mammal bycatch of 0.13 animals per set (10 marine 

mammals in 77 observed sets; Sosa-Nishizaki et al. 1993). This overall mortality rate is similar to that 

observed in California driftnet fisheries during 1990-95 (0.14 marine mammals per set; Julian and Beeson, 

1998), but species-specific information is not available for the Mexican fisheries. Previous efforts to 

convert the Mexican swordfish driftnet fishery to a longline fishery have resulted in a mixed-fishery, with 

20 vessels alternately using longlines or driftnets, 23 using driftnets only, 22 using longlines only, and 

seven with unknown gear type (Berdegué 2002). 

Table 1. Summary of available information on the incidental mortality and injury of long-beaked common 

dolphins (California Stock) and prorated unidentified common dolphins in commercial fisheries that might 

take this species. All observed entanglements resulted in the death of the animal. The observer program 

for the set gillnet fishery was discontinued during 1994 and later resumed in Monterey Bay from 1999-

2000. Coefficients of variation for mortality estimates are provided in parentheses, when available. Mean 

annual takes are based on 2000-2004 data unless noted otherwise. n/a = information not available. 

Fishery Name Data Type Year(s) 

Percent 

Observer 

Coverage

Observed Estimated Annual 

Mortality

Mean 

Annual Takes 

(CV in 

parentheses)

CA/OR thresher 

shark/swordfish drift 

gillnet fishery

observer 

2000 

2001 

2002 

2003 

2004 

22.9% 

20.4% 

22.1% 

20.2% 

20.6% 

1 

0 

4 

0 

0 

4 (1.08) 

0 

18 (0.79) 

0 

0 

4.4 (1.69) 

CA small mesh drift 

gillnet fishery for white 

seabass, yellowtail, 

barracuda, and tuna 

observer 

2000 

2001 

2002 

2003 

2004 

not observed 

not observed 

11.5% 

10.4% 

17.6% 

n/a 

n/a 

0 

1 

1 

n/a 

n/a 

0 (n/a) 

9 (0.78) 

5 (1.18) 

4.7 (0.98) 

Common dolphins, species not determined 

CA angel shark/ halibut 

and other species large 

mesh (>3.5in) set gillnet 

fishery2

MMAP 

selfreporting 

2000 

2001 

2002 

2003 

2004 

- 

- 

- 

- 

- 

- 

- 

0 

0 

0 

0 

1 

0 

0 

0 

0 

n/a 

(n/a) 

≥0.2 (n/a) 

Undetermined strandings 2000-2004

 Sixteen common dolphins (six unidentified and ten 

longbeaked common dolphin) stranded with evidence of 

fishery interactions. Two long-beaked common 

dolphins stranded with portions of ‘halibut’ gillnet 

around animal 

≥3.2 (n/a) 

Minimum total annual takes 12.5 (0.70) 

1 Observer coverage in the small mesh drift gillnet fishery was estimated from logbook records. Logbook effort totaled 192, 134, 191, 

201, and 125 sets for 2000 through 2004, respectively. The fishery was not observed in 2000 and 2001 and annual fishery mortality is 

calculated based on the three-year average from 2002-2004. 

2

The set gillnet fishery was observed from 1991-94 and then only in Monterey Bay during 1999-2000, where 20-25% of the local 

fishery was observed. No estimates of current mortality are available for this fishery because of a lack of recent observer coverage.

Other Mortality

 In the eastern tropical Pacific, 'northern common dolphins' have been incidentally killed in 

international tuna purse seine fisheries since the late 1950's. Cooperative international management 

programs have dramatically reduced overall dolphin mortality in these fisheries during the last decade 

(Joseph 1994). Between 2000-2004, annual fishing mortality of northern common dolphins (potentially 

including both short-beaked and long-beaked common dolphins) ranged between 54 and 159 animals, 

with an average of 102 (IATTC, 2006). Although it is unclear whether these animals are part of the same 

118
population as short-beaked common dolphins found off California, they are managed separately under a 

section of the MMPA written specifically for the management of dolphins involved in eastern tropical 

Pacific tuna fisheries.

STATUS OF STOCK

 The status of long-beaked common dolphins in California waters relative to OSP is not known, 

and there are insufficient data to evaluate potential trends in abundance of this species of common dolphin. 

No habitat issues are known to be of concern for this species. They are not listed as "threatened" or 

"endangered" under the Endangered Species Act nor as "depleted" under the MMPA. The average annual 

human-caused mortality from 2000-2004 (12.5 animals) exceeds the PBR (11), and therefore they are 

classified as a "strategic" stock under the MMPA. The average total fishery mortality and injury for longbeaked common dolphins exceeds the PBR and, therefore, cannot be considered to be insignificant and 

approaching zero mortality and serious injury rate. 

REFERENCES

Barlow, J. 1995. The abundance of cetaceans in California waters. Part I: Ship surveys in summer and fall 

of 1991. Fish. Bull. 93:1-14. 

Barlow, J. 1997. Preliminary estimates of cetacean abundance off California, Oregon and Washington 

based on a 1996 ship survey and comparisons of passing and closing modes. Administrative 

Report LJ-97-11, Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. 

Box 271, La Jolla, CA 92038. 25p. 

Barlow, J. and G. A. Cameron. 2003. Field experiments show that acoustic pingers reduce marine mammal 

bycatch in the California drift gillnet fishery. Marine Mammal Science 19(2):265-283. 

Barlow, J., K. A. Forney, P. S. Hill, R. L. Brownell, Jr., J. V. Carretta, D. P. DeMaster, F. Julian, M. S. 

Lowry, T. Ragen, and R. R. Reeves. 1997. U.S. Pacific Marine Mammal Stock Assessments: 

1996. U.S. Dep. Commer., NOAA Tech. Memo. NMFS-SWFSC-248. 223p. 

Barlow, J. and T. Gerrodette. 1996. Abundance of cetaceans in California waters based on 1991 and 1993 

ship surveys. U.S. Dep. Commer., NOAA Tech. Memo. NMFS-SWFSC-233. 

Barlow, J. 2003. Preliminary estimates of the abundance of cetaceans along the U.S. west coast: 

1991_2001. Southwest Fisheries Science Center Administrative Report LJ_03_03. Available 

from SWFSC, 8604 La Jolla Shores Dr., La Jolla CA 92037. 31p. 

Berdegué, J. 2002. Depredación de las especies pelágicas reservadas a la pesca deportiva y especies en 

peligro de extinción con uso indiscriminado de artes de pesca no selectivas (palangres, FAD's, 

trampas para peces y redes de agallar fijas y a la deriva) por la flota palangrera Mexicana. 

Fundación para la conservación de los picudos. A.C. Mazatlán, Sinaloa, 21 de septiembre. 

Carretta, J.V. and S.J. Chivers. 2004. Preliminary estimates of marine mammal mortality and biological 

sampling of cetaceans in California gillnet fisheries for 2003. Paper SC/56/SM1 presented to the 

IWC Scientific Committee, June 2004 (unpublished). [Available from Southwest Fisheries 

Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 

92037, USA]. 

Carretta, J.V., S.J. Chivers, and K. Danil. 2005a. Preliminary estimates of marine mammal bycatch, 

mortality, and biological sampling of cetaceans in California gillnet fisheries for 2004. 

Administrative Report LJ-05-10, available from Southwest Fisheries Science Center, 8604 La 

Jolla Shores Drive, La Jolla, California, 92037. 17 p. 

Carretta, J.V., T. Price, D. Petersen, and R. Read. 2005b. Estimates of marine mammal, sea turtle, and 

seabird mortality in the California drift gillnet fishery for swordfish and thresher shark, 1996-

2002. Marine Fisheries Review 66(2):21-30. 

Forney, K. A., J. Barlow and J. V. Carretta. 1995. The abundance of cetaceans in California waters. Part 

II: Aerial surveys in winter and spring of 1991 and 1992. Fish. Bull. 93:15-26. 

Forney, K.A. 2007. Preliminary estimates of cetacean abundance along the U.S. west coast and within 

four National Marine Sanctuaries during 2005. U.S. Department of Commerce, NOAA Technical 

Memorandum NMFS-SWFSC-406. 27p. 

Heyning, J. E. and W. F. Perrin. 1994. Evidence for two species of common dolphins (Genus Delphinus) 

from the eastern North Pacific. Contr. Nat. Hist. Mus. L.A. County, No. 442. 

Hill, P. S. and D. P. DeMaster. 1998. Alaska Marine Mammal Stock Assessments, 1998. U.S. Dep. 

Commer., NOAA Tech. Memo. NMFS-AFSC-97. 166 pp. 

119
Holts, D. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores 

Drive, La Jolla, CA 92037. 

Holts, D. and O. Sosa-Nishizaki. 1998. Swordfish, Xiphias gladius, fisheries of the eastern North Pacific 

Ocean. In: I. Barrett, O. Sosa-Nishizaki and N. Bartoo (eds.). Biology and fisheries of swordfish, 

Xiphias gladius. Papers from the International Symposium on Pacific Swordfish, Ensenada 

Mexico, 11-14 December 1994. U.S. Dep. Commer., NOAA Tech. Rep. NMFS 142, 276 pp. 

IATTC. 2006. Annual Report of the Inter-American Tropical Tuna Commission, 2004, La Jolla, 

California. 96p. 

Joseph, J. 1994. The tuna-dolphin controversy in the eastern Pacific Ocean: biological, economic and 

political impacts. Ocean Dev. Int. Law 25:1-30. 

Julian, F. 1997. Cetacean mortality in California gill net fisheries: Preliminary estimates for 1996. Paper 

SC/49/SM02 presented to the International Whaling Commission, 1997 (unpublished). 13 pp. 

Julian, F. and M. Beeson. 1998. Estimates of mammal, turtle and bird mortality for two California gillnet 

fisheries: 1990-1995. Fish. Bull. 96:271-284. 

NMFS, Southwest Fisheries Science Center, P.O. Box 271, La Jolla, CA 92038-027. 

NMFS, Southwest Region, 501 West Ocean Blvd, Long Beach, CA 90802_4213. 

Perrin, W. F., M. D. Scott, G. J. Walker and V. L. Cass. Review of geographical stocks of tropical 

dolphins (Stenella spp. and Delphinus delphis) in the eastern Pacific. NOAA Technical Report 

NMFS 28. Available from NMFS, Southwest Fisheries Science Center, P.O. Box 271, La Jolla, 

California, 92038. 28p. 

Rosel, P. E., A. E. Dizon and J. E. Heyning. 1994. Population genetic analysis of two forms of the 

common dolphin (genus Delphinus) utilizing mitochondrial DNA control region sequences. 

Marine Biology 119:159-167. 

Sosa-Nishizaki, O., R. De la Rosa-Pacheco, R. Castro-Longoria, M. Grijalva Chon, and J. De la Rosa 

Velez. 1993. Estudio biologico pesquero del pez (Xiphias gladius) y otras especies de picudos 

(marlins y pez vela). Rep. Int. CICESE, CTECT9306. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the 

GAMMS Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. 

Memo. NMFS-OPR-12. 93 pp. 

120
Revised 10/30/2007 

NORTHERN RIGHT-WHALE DOLPHIN (Lissodelphis borealis): 

California/Oregon/Washington Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

 Northern right-whale 

dolphins are endemic to temperate 

waters of the North Pacific Ocean. 

Off the U.S. west coast, they have 

been seen primarily in shelf and 

slope waters (Figure 1), with 

seasonal movements into the 

Southern California Bight 

(Leatherwood and Walker 1979; 

Dohl et al. 1980; 1983; NMFS, 

unpublished data). Sighting patterns 

from recent aerial and shipboard 

surveys conducted in California, 

Oregon and Washington during 

different seasons (Green et al. 1992; 

1993; Forney et al. 1995; Barlow 

1995) suggest seasonal north-south 

movements, with animals found 

primarily off California during the 

colder water months and shifting 

northward into Oregon and 

Washington as water temperatures 

increase in late spring and summer 

(Green et al. 1992; Forney 1994; 

Forney and Barlow 1998). The 

southern end of this population's 

range is not well-documented, but 

during cold-water periods, they 

probably range into Mexican waters 

off northern Baja California. 

Genetic analyses have not found 

statistically significant differences 

between northern right-whale dolphins from 

the U.S. West coast and other areas of the 

North Pacific (Dizon et al. 1994); however, 

power analyses indicate that the ability to 

detect stock differences for this species is 

poor, given traditional statistical error levels 

(Dizon et al. 1995). Although northern 

right-whale dolphins are not restricted to 

U.S. territorial waters, there are currently no 

international agreements for cooperative 

management. For the Marine Mammal Protection Act (MMPA) stock assessment reports, there is a single 

management stock including only animals found within the U.S. Exclusive Economic Zone of California, 

Oregon and Washington. 

OREGON

WASHINGTON

CALIFORNIA

POPULATION SIZE

 The previous best estimates of abundance for northern right-whale dolphins (Barlow et al. 1997) 

were based on winter/spring 1991-92 aerial surveys (Forney et al. 1995) off California, which were 

presumed to include northern right-whale dolphins that are found off Oregon and Washington during 

Figure 1. Northern right whale dolphin 

sightings based on aerial and shipboard surveys 

off California, Oregon, and Washington, 1991- 

2005 (see Appendix 2 for data sources and 

information on timing and location of survey 

effort). Dashed line represents the U.S. EEZ, 

thin lines indicates completed transect effort of 

all surveys combined. Key: • = summer/autumn 

ship-based sightings; + = winter/spring aerialbased sightings. 

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

45°0'0"N

40°0'0"N

121
summer and fall. Two summer/fall shipboard surveys were conducted within 300 nmi of the coasts of 

California, Oregon and Washington in 2001 (Barlow 2003) and 2005 (Forney 2007). The distribution of 

northern right-whale dolphins throughout this region is highly variable, apparently in response to 

oceanographic changes on both seasonal and interannual time scales (Forney and Barlow 1998). As 

oceanographic conditions vary, northern right-whale dolphins may spend time outside the U.S. Exclusive 

Economic Zone, and therefore a multi-year average abundance estimate is the most appropriate for 

management within U.S. waters. The 2001-2005 geometric mean abundance estimate for California, 

Oregon and Washington waters based on the two ship surveys is 15,305 (CV= 0.32) northern right-whale 

dolphins (Barlow 2003, Forney 2007). 

Minimum Population Estimate

 The log-normal 20th percentile of the 2001-2005 average abundance estimate is 11,754 northern 

right-whale dolphins. 

Current Population Trend

 Estimates of northern right whale dolphin abundance from surveys conducted in 1991/93, 1996, 

and 2001 in California waters were 9,929 (CV = 0.49); 14,593 (0.55); and 10,915 (0.41), respectively 

(Barlow 2003). Abundance estimates for all California, Oregon, and Washington waters from 1996, 2001, 

and 2005 surveys were 19,619 (0.43), 21,104 (0.30), and 11,100 (0.60), respectively (Barlow 2003, Forney 

2007). Currently, there is no evidence of a trend in abundance for this stock. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No information on current or maximum net productivity rates is available for northern right-whale 

dolphins off the U.S. west coast. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum 

population size (11,754) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times

a recovery factor of 0.48 (for a species of unknown status with a mortality rate CV >0.30 and ≤ 0.60; Wade 

and Angliss 1997), resulting in a PBR of 113 northern right-whale dolphins per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

 A summary of recent fishery mortality and injury for this stock of northern right-whale dolphin is 

shown in Table 1. More detailed information on these fisheries is provided in Appendix 1. Mortality 

estimates for the California drift gillnet fishery are included for the five most recent years of monitoring, 

2000-2004 (Carretta and Chivers 2004, Carretta et al. 2005a, 2005b). After the 1997 implementation of a 

Take Reduction Plan, which included skipper education workshops and required the use of pingers and 

minimum 6-fathom extenders, overall cetacean entanglement rates in the drift gillnet fishery dropped 

considerably (Barlow and Cameron 2003). However, because of interannual variability in entanglement 

rates and the relative rarity of northern right-whale dolphin entanglements, additional years of data will be 

required to fully evaluate the effectiveness of pingers for reducing mortality of this particular species. 

Entanglement rates for this species may be related to oceanographic conditions, as lower entanglement 

rates have been observed during warm-water periods, such as El Niño (Figure 2). Mean annual takes in 

Table 1 are based on 2000-2004 data. This results in an average estimate of 18 (CV= 0.31) northern rightwhale dolphins taken annually. 

Table 1. Summary of available information on the incidental mortality and injury of northern right-whale 

dolphins (California/Oregon/Washington Stock) in commercial fisheries that might take this species. All 

observed entanglements of northern right-whale dolphins resulted in the death of the animal. Coefficients 

of variation for mortality estimates are provided in parentheses. Mean annual takes are based on 2000-

2004 data unless noted otherwise. 

122
Fishery Name Data Type Year(s) 

Percent 

Observer 

Coverage

Observed 

Mortality

Estimated Annual 

Mortality

Mean 

Annual Takes 

(CV in 

parentheses) 

CA/OR thresher 

shark/swordfish drift 

gillnet fishery

observer 

data 

2000 

2001 

2002 

2003 

2004 

22.9% 

20.4% 

22.1% 

20.2% 

20.6% 

11 

5 

2 

1 

1 

48 ( 0.48) 

25 (0. 0.57) 

9 (0.70) 

5 (1.00) 

5 (0.99) 

18 (0.31) 

Minimum total annual takes 18 (0.31) 

 

0

0.005

0.01

0.015

0.02

0.025

0.03

1990

1991

1992

1993

1994

1995

1996

1997

1998

1999

2000

2001

2002

2003

2004

Year

Kill/Day

No pingers Pingers

Figure 2. Kill rates of northern right whale dolphin per set fished in the California drift gillnet fishery for 

swordfish and thresher shark, 1990-2004. Kill rates include observations from pingered and unpingered 

sets. Pingers were not used from 1990-95 and were used experimentally in 1996 and 1997. For the period 

1998-2004, over 99% of all observed sets utilized pingers. 

 

 Drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of Baja 

California, Mexico and may take animals from this population. Quantitative data are available only for the 

Mexican swordfish drift gillnet fishery, which uses vessels, gear, and operational procedures similar to 

those in the U.S. drift gillnet fishery, although nets may be up to 4.5 km long (Holts and Sosa-Nishizaki 

1998). The fleet increased from two vessels in 1986 to 31 vessels in 1993 (Holts and Sosa-Nishizaki 1998). 

The total number of sets in this fishery in 1992 can be estimated from data provided by these authors to be 

approximately 2700, with an observed rate of marine mammal bycatch of 0.13 animals per set (10 marine 

mammals in 77 observed sets; Sosa-Nishizaki et al. 1993). This overall mortality rate is similar to that 

observed in California driftnet fisheries during 1990-95 (0.14 marine mammals per set; Julian and Beeson, 

1998), but species-specific information is not available for the Mexican fisheries. Previous efforts to 

convert the Mexican swordfish driftnet fishery to a longline fishery have resulted in a mixed-fishery, with 

20 vessels alternately using longlines or driftnets, 23 using driftnets only, 22 using longlines only, and 

seven with unknown gear type (Berdegué 2002). 

STATUS OF STOCK

 The status of northern right-whale dolphins in California, Oregon and Washington relative to OSP 

is not known, and there are insufficient data to evaluate trends in abundance. No habitat issues are known 

to be of concern for this species. They are not listed as "threatened" or "endangered" under the Endangered 

Species Act nor as "depleted" under the MMPA. The average annual human-caused mortality in 2000-

2004 (18 animals) is estimated to be less than the PBR (113), and therefore they are not classified as a 

"strategic" stock under the MMPA. The total fishery mortality and serious injury for northern right-whale 

dolphins is greater than 10% of the calculated PBR and, therefore, cannot be considered to be insignificant 

and approaching zero mortality and serious injury rate. 

123
REFERENCES

Barlow, J. 1995. The abundance of cetaceans in California waters. Part I: Ship surveys in summer and fall 

of 1991. Fish. Bull. 93:1-14. 

Barlow, J. 1997. Preliminary estimates of cetacean abundance off California, Oregon and Washington 

based on a 1996 ship survey and comparisons of passing and closing modes. Administrative 

Report LJ-97-11, Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. 

Box 271, La Jolla, CA 92038. 25p. 

Barlow, J. and G. A. Cameron. 2003. Field experiments show that acoustic pingers reduce marine mammal 

bycatch in the California drift gillnet fishery. Marine Mammal Science 19(2):265-283. 

Barlow, J., K. A. Forney, P. S. Hill, R. L. Brownell, Jr., J. V. Carretta, D. P. DeMaster, F. Julian, M. S. 

Lowry, T. Ragen, and R. R. Reeves. 1997. U.S. Pacific Marine Mammal Stock Assessments: 

1996. U.S. Dep. Commer., NOAA Tech. Memo. NMFS-SWFSC-248. 223p. 

Barlow, J. and T. Gerrodette. 1996. Abundance of cetaceans in California waters based on 1991 and 1993 

ship surveys. U.S. Dep. Commer., NOAA Tech. Memo. NMFS-SWFSC-233. 

Barlow, J. 2003. Preliminary estimates of the abundance of cetaceans along the U.S. west coast: 

1991_2001. Southwest Fisheries Science Center Administrative Report LJ_03_03. Available 

from SWFSC, 8604 La Jolla Shores Dr., La Jolla CA 92037. 31p. 

Berdegué, J. 2002. Depredación de las especies pelágicas reservadas a la pesca deportiva y especies en 

peligro de extinción con uso indiscriminado de artes de pesca no selectivas (palangres, FAD's, 

trampas para peces y redes de agallar fijas y a la deriva) por la flota palangrera Mexicana. 

Fundación para la conservación de los picudos. A.C. Mazatlán, Sinaloa, 21 de septiembre. 

Carretta, J.V. and S.J. Chivers. 2004. Preliminary estimates of marine mammal mortality and biological 

sampling of cetaceans in California gillnet fisheries for 2003. Paper SC/56/SM1 presented to the 

IWC Scientific Committee, June 2004 (unpublished). [Available from Southwest Fisheries 

Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 

92037, USA]. 

Carretta, J.V., S.J. Chivers, and K. Danil. 2005a. Preliminary estimates of marine mammal bycatch, 

mortality, and biological sampling of cetaceans in California gillnet fisheries for 2004. 

Administrative Report LJ-05-10, available from Southwest Fisheries Science Center, 8604 La 

Jolla Shores Drive, La Jolla, California, 92037. 17 p. 

Carretta, J.V., T. Price, D. Petersen, and R. Read. 2005b. Estimates of marine mammal, sea turtle, and 

seabird mortality in the California drift gillnet fishery for swordfish and thresher shark, 1996-

2002. Marine Fisheries Review 66(2):21-30. 

Dizon, A., C. LeDuc, and R. LeDuc. 1994. Intraspecific structure of the northern right-whale dolphin 

(Lissodelphis borealis): The power of an analysis of molecular variation for differentiating 

genetic stocks. CalCOFI Rep. 35:61-67. 

Dizon, A. E., G. M. O'Corry-Crowe, and B. L. Taylor. (1995). Why statistical power is necessary to link 

analyses of molecular variation to decisions about population structure. pp. 288-294 In: J. L. 

Neilsen (ed.), Evolution and the Aquatic Ecosystem: Defining Unique Units in Population 

Conservation. American Fisheries Society Symposium 17. 

Dohl, T. P., R. C. Guess, M. L. Duman, and R. C. Helm. 1983. Cetaceans of central and northern 

California, 1980-1983: Status, abundance and distribution. OCS Study MMS 84-0045. Minerals 

Management Service Contract # 14-12-0001-29090. 284p. 

Dohl, T. P., K. S. Norris, R. C. Guess, J. D. Bryant, and M. W. Honig. 1980. Summary of marine mammal 

and seabird surveys of the Southern California Bight area, 1975-1978. Part II. Cetacea of the 

Southern California Bight. Final Report to the Bureau of Land Management, NTIS Rep. No. 

PB81248189. 414p. 

Forney, K. A. 1994. Recent information on the status of odontocetes in Californian waters. NOAA 

Technical Memorandum NMFS, NOAA-TM-NMFS-SWFSC-202. Available from NMFS, 

Southwest Fisheries Science Center, P.O. Box 271, La Jolla, California, USA. 

Forney, K. A. and J. Barlow. 1998. Seasonal patterns in the abundance and distribution of California 

cetaceans, 1991-92. Mar. Mamm. Sci. 14:460-489. 

Forney, K. A., J. Barlow and J. V. Carretta. 1995. The abundance of cetaceans in California waters. Part 

II: Aerial surveys in winter and spring of 1991 and 1992. Fish. Bull. 93:15-26. 

124
Forney, K.A. 2007. Preliminary estimates of cetacean abundance along the U.S. west coast and within 

four National Marine Sanctuaries during 2005. U.S. Department of Commerce, NOAA Technical 

Memorandum NMFS-SWFSC-xxx. 

Green, G., J. J. Brueggeman, R. A. Grotefendt, C. E. Bowlby, M. L. Bonnell, and K. C. Balcomb, III. 

1992. Cetacean distribution and abundance off Oregon and Washington. Ch. 1. In: Oregon and 

Washington Marine Mammal and Seabird Surveys. OCS Study 91-0093. Final Report prepared 

for Pacific OCS Region, Minerals Management Service, U.S. Department of the Interior, Los 

Angeles, California. 

Green, G., R. A. Grotefendt, M. A. Smultea, C. E. Bowlby, and R. A. Rowlett. 1993. Delphinid aerial 

surveys in Oregon and Washington waters. Final Report prepared for NMFS, National Marine 

Mammal Laboratory, 7600 Sand Point Way, NE, Seattle, Washington, 98115, Contract 

#50ABNF200058. 

Holts, D. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores 

Drive, La Jolla, CA 92037. 

Holts, D. and O. Sosa-Nishizaki. 1998. Swordfish, Xiphias gladius, fisheries of the eastern North Pacific 

Ocean. In: I. Barrett, O. Sosa-Nishizaki and N. Bartoo (eds.). Biology and fisheries of swordfish, 

Xiphias gladius. Papers from the International Symposium on Pacific Swordfish, Ensenada 

Mexico, 11-14 December 1994. U.S. Dep. Commer., NOAA Tech. Rep. NMFS 142, 276 p. 

Julian, F. and M. Beeson. 1998. Estimates of mammal, turtle and bird mortality for two California gillnet 

fisheries: 1990-1995. Fish. Bull. 96:271-284. 

Leatherwood, S. and W. A. Walker. 1979. The northern right-whale dolphin Lissodelphis borealis Peale 

in the eastern North Pacific. In: Winn, H. E. and B. L. Olla (eds.), Behavior of Marine Mammals, 

p. 85-141. Plenum Press, New York - London. 

National Marine Fisheries Service, Southwest Fisheries Science Center. Unpublished data. 

Sosa-Nishizaki, O., R. De la Rosa-Pacheco, R. Castro-Longoria, M. Grijalva Chon, and J. De la Rosa 

Velez. 1993. Estudio biologico pesquero del pez (Xiphias gladius) y otras especies de picudos 

(marlins y pez vela). Rep. Int. CICESE, CTECT9306. 

Stick, K. C. and Hreha, L. 1989. Summary of the 1988 Washington/Oregon experimental thresher shark 

gill net fishery. State of Washington, Department of Fisheries, Progress Report 275. 40p. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the 

GAMMS Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. 

Memo. NMFS-OPR-12. 93 pp. 

125
Revised 10/30/2007

KILLER WHALE (Orcinus orca): 

Eastern North Pacific Offshore Stock 

STOCK DEFINITION AND 

GEOGRAPHIC RANGE 

 Killer whales have been 

observed in all oceans and seas of 

the world (Leatherwood and 

Dahlheim 1978). Although reported 

from tropical and offshore waters, 

killer whales prefer the colder 

waters of both hemispheres, with 

greatest abundances found within 

800 km of major continents 

(Mitchell 1975). Along the west 

coast of North America, killer 

whales occur along the entire 

Alaskan coast (Braham and 

Dahlheim 1982), in British 

Columbia and Washington inland 

waterways (Bigg et al. 1990), and 

along the outer coasts of 

Washington, Oregon and California 

(Green et al. 1992; Barlow 1995, 

1997; Forney et al. 1995). Seasonal 

and year-round occurrence have 

been noted for killer whales 

throughout Alaska (Braham and 

Dahlheim 1982) and in the 

intracoastal waterways of British 

Columbia and Washington, where 

pods have been labeled as 'resident', 

'transient' and ‘offshore’ (Bigg et al. 

1990, Ford et al. 1994) based on 

aspects of morphology, ecology, genetics 

and behavior (Ford and Fisher 1982; Baird 

and Stacey 1988; Baird et al. 1992, Hoelzel 

et al. 1998). Through examination of 

photographs of recognizable individuals and 

pods, movements of whales between 

geographical areas have been documented. 

For example, whales identified in Prince 

William Sound have been observed near 

Kodiak Island (Heise et al. 1991) and whales identified in Southeast Alaska have been observed in Prince 

William Sound, British Columbia, and Puget Sound (Leatherwood et al. 1990, Dahlheim et al. 1997). 

Movements of killer whales between the waters of Southeast Alaska and central California have also been 

documented (Goley and Straley 1994). 

OREGON

WASHINGTON

CALIFORNIA

 Offshore killer whales have more recently also been identified off the coasts of California, 

Oregon, and rarely, in Southeast Alaska (Ford et al. 1994, Black et al. 1997, Dahlheim et al. 1997). They 

apparently do not mix with the transient and resident killer whale stocks found in these regions (Ford et al. 

1994, Black et al. 1997). Studies indicate the ‘offshore’ type, although distinct from the other types 

(‘resident’ and ‘transient’), appears to be more closely related genetically, morphologically, behaviorally, 

and vocally to the ‘resident’ type killer whales (Black et al. 1997, Hoelzel et al. 1998; J. Ford, pers. comm.; 

Figure 1. Killer whale sightings based on aerial 

and shipboard surveys off California, Oregon 

and Washington, 1991- 2005 (see Appendix 2 

for data sources and information on timing and 

location of survey effort). Sightings include 

killer whales from all stocks found in this region. 

Dashed line represents the U.S. EEZ, thin lines 

indicate completed transect effort of all surveys 

combined. 

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

45°0'0"N

40°0'0"N

126
L. Barrett-Lennard, pers. comm.). Based on data regarding association patterns, acoustics, movements, 

genetic differences, and potential fishery interactions, five killer whale stocks are recognized within the 

Pacific U.S. EEZ 1) the Eastern North Pacific Northern Resident stock - occurring from British Columbia 

through Alaska, 2) the Eastern North Pacific Southern Resident stock - occurring within the inland waters 

of Washington and southern British Columbia, 3) the Eastern North Pacific Transient stock - occurring 

from Alaska through California, 4) the Eastern North Pacific Offshore stock - occurring from Southeast 

Alaska through California (this report), and 5) the Hawaiian stock. ‘Offshore’ whales in Canadian waters 

are considered part of the Eastern North Pacific Offshore stock. The Stock Assessment Reports for the 

Alaska Region contain assessments of the Eastern North Pacific Northern Resident and transient stocks, 

and the most recent assessment for the Hawaii Stock is included in this volume. 

POPULATION SIZE

 Off British Columbia, approximately 200 offshore killer whales were identified between 1989 and 

1993 (Ford et al. 1994), and 20 of these individuals have also been seen off California (Black et al. 1997). 

Using only good quality photographs that clearly show characteristics of the dorsal fin and saddle patch 

region, an additional 11 offshore killer whales that were not previously known have been identified off the 

California coast, bringing the total number of known individuals in this population to 211. This is certainly 

an underestimate of the total population size, because not all animals in this population have been 

photographed. In the future, it may be possible estimate the total abundance of this transboundary stock 

using mark-recapture analyses based on individual photographs. Based on summer/fall shipboard linetransect surveys in 2001 (Barlow 2003) and 2005 (Forney 2007), the total number of killer whales within 

300 nmi of the coasts of California, Oregon and Washington is estimated to be 1,214 animals (CV= 0.29). 

There is currently no way to reliably distinguish the different stocks of killer whales from sightings at sea, 

but photographs of individual animals can provide a rough estimate of the proportion of whales in each 

stock. A total of 161 individual killer whales photographed off California and Oregon have been 

determined to belong to the transient (105 whales) and offshore (56 whales) stocks (Black et al. 1997). 

Using these proportions to prorate the line transect abundance estimate yields an estimate of 56/161 * 

1,214 = 422 offshore killer whales along the U.S. west coast. This is expected to be a conservative 

estimate of the number of offshore killer whales, because offshore whales apparently are less frequently 

seen near the coast (Black et al. 1997), and therefore photographic sampling may be biased towards 

transient whales. For stock assessment purposes, this combined value is currently the best available 

estimate of abundance for offshore killer whales off the coasts of California, Oregon and Washington. 

Minimum Population Estimate

 The total number of known offshore killer whales along the U.S. West coast, Canada and Alaska 

is 211 animals, but it is not known what proportion of time this transboundary stock spends in U.S. waters, 

and therefore this number is difficult to work with for PBR calculations. A minimum abundance estimate 

for all killer whales along the coasts of California, Oregon and Washington can be estimated from the 

2001-2005 line-transect surveys as the 20th percentile of the mean 2001-2005 abundance estimate, or 953 

killer whales. Using the same prorating as above, a minimum of 56/161 * 953 = 331 offshore killer 

whales are estimated to be in U.S. waters off California, Oregon and Washington. 

Current Population Trend

 No information is available regarding trends in abundance of Eastern North Pacific offshore killer 

whales. 

 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No information on current or maximum net productivity rates is available for killer whales in this 

region. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum 

population size (331) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a 

recovery factor of 0.50 (for a species of unknown status with no known fishery mortality; Wade and 

Angliss 1997), resulting in a PBR of 3.3 offshore killer whales per year. 

127
HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

 A summary of information on fisheries that may take animals from this killer whale stock is 

shown in Table 1 (Carretta and Chivers 2004, Carretta et al. 2005a, 2005b). More detailed information on 

these fisheries is provided in Appendix 1. In the California drift gillnet fishery, no offshore killer whales 

have been observed entangled (Julian 1997; Julian and Beeson 1998; Cameron and Forney 1999, 2000; 

Carretta and Chivers 2004, Carretta et al. 2005a, 2005b), but one killer whale from the Eastern North 

Pacific Transient Stock was observed taken in 1995, and offshore killer whales may also occasionally be 

entangled. Additional potential sources of killer whale mortality are set gillnets and longlines. In 

California, an observer program between July 1990 and December 1994 monitored 5-15% of all sets in the 

large mesh (>3.5") set gillnet fishery for halibut and angel sharks, and no killer whales were observed 

taken. Based on observations for longline fisheries in other regions (i.e. Alaska; Yano and Dahlheim 

1995), fishery interactions may also occur with U.S. West coast pelagic longline fisheries, but no such 

interactions have been documented to date. 

Table 1. Summary of available information on the incidental mortality and injury of killer whales (Eastern 

North Pacific Offshore Stock) in commercial fisheries that might take this species. Mean annual takes are 

based on 2000-2004 data unless noted otherwise. 

Fishery Name Data Type Year(s) 

Percent 

Observer 

Coverage

Observed 

Mortality

Estimated An ual n

Mortality

Mean 

Annual Takes 

(CV in 

parentheses) 

CA/OR thresher 

shark/swordfish drift 

gillnet fishery

observer 

data

2000 

2001 

2002 

2003 

2004 

22.9% 

20.4% 

22.1% 

20.2% 

20.6% 

0 

0 

0 

0

0

0 

0 

0 

0

0

0

Minimum total annual takes 0

 

Drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of Baja 

California, Mexico and may take animals from this population. Quantitative data are available only for the 

Mexican swordfish drift gillnet fishery, which uses vessels, gear, and operational procedures similar to 

those in the U.S. drift gillnet fishery, although nets may be up to 4.5 km long (Holts and Sosa-Nishizaki 

1998). The fleet increased from two vessels in 1986 to 31 vessels in 1993 (Holts and Sosa-Nishizaki 1998). 

The total number of sets in this fishery in 1992 can be estimated from data provided by these authors to be 

approximately 2700, with an observed rate of marine mammal bycatch of 0.13 animals per set (10 marine 

mammals in 77 observed sets; Sosa-Nishizaki et al. 1993). This overall mortality rate is similar to that 

observed in California driftnet fisheries during 1990-95 (0.14 marine mammals per set; Julian and Beeson, 

1998), but species-specific information is not available for the Mexican fisheries. Previous efforts to 

convert the Mexican swordfish driftnet fishery to a longline fishery have resulted in a mixed-fishery, with 

20 vessels alternately using longlines or driftnets, 23 using driftnets only, 22 using longlines only, and 

seven with unknown gear type (Berdegué 2002). 

Historical mortality

 California coastal whaling operations killed five killer whales between 1962 and 1967 (Rice 

1974). An additional killer whale was taken by whalers in British Columbian waters (Hoyt 1981). It is 

unknown whether any of these animals belonged to the Eastern North Pacific Offshore stock. 

STATUS OF STOCK

 The status of killer whales in California in relation to OSP is unknown, and there are insufficient 

data to evaluate trends in abundance. No habitat issues are known to be of concern for this species. They 

are not listed as "threatened" or "endangered" under the Endangered Species Act nor as "depleted" under 

the MMPA. There has been no documented human-caused mortality of this stock, and therefore they are 

not classified as a "strategic" stock under the MMPA. The total fishery mortality and serious injury for 

128
offshore killer whales is zero and can be considered to be insignificant and approaching zero mortality and 

serious injury rate. 

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NOAA Tech. Memo. NMFS-SWFSC-247. 174p. 

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Cameron, G.A. and K.A. Forney. 2000. Preliminary estimates of cetacean mortality in California/Oregon 

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sampling of cetaceans in California gillnet fisheries for 2003. Paper SC/56/SM1 presented to the 

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Carretta, J.V., T. Price, D. Petersen, and R. Read. 2005b. Estimates of marine mammal, sea turtle, and 

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2002. Marine Fisheries Review 66(2):21-30. 

129
Dahlheim, M. E., D. Ellifrit, and J. Swenson. 1997. Killer Whales of Southeast Alaska: A Catalogue of 

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British Columbia. Rep. Int. Whal. Commn 32:671-679. 

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II: Aerial surveys in winter and spring of 1991 and 1992. Fish. Bull. 93:15-26. 

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four National Marine Sanctuaries during 2005. U.S. Department of Commerce, NOAA Technical 

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Goley, P. D., and J. M. Straley. 1994. Attack on gray whales (Eschrichtius robustus) in Monterey Bay, 

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Washington Marine Mammal and Seabird Surveys. OCS Study 91-0093. Final Report prepared 

for Pacific OCS Region, Minerals Management Service, U.S. Department of the Interior, Los 

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Oceanic Society, Homer, AK. Published for the National Marine Mammal Laboratory, 7600 Sand 

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(Orcinus orca) in the Eastern North Pacific, and genetic differentiation between foraging 

specialists. J. Heredity 89:121-128. 

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CA 92038. 

Holts, D. and O. Sosa-Nishizaki. 1998. Swordfish, Xiphias gladius, fisheries of the eastern North Pacific 

Ocean. In: I. Barrett, O. Sosa-Nishizaki and N. Bartoo (eds.). Biology and fisheries of swordfish, 

Xiphias gladius. Papers from the International Symposium on Pacific Swordfish, Ensenada 

Mexico, 11-14 December 1994. U.S. Dep. Commer., NOAA Tech. Rep. NMFS 142, 276 p. 

Hoyt, E. 1981. The Whale Called Killer. E. P. Dutton, New York. 

Julian, F. 1997. Cetacean mortality in California gill net fisheries: Preliminary estimates for 1996. Paper 

SC/49/SM02 presented to the International Whaling Commission, 1997 (unpublished). 13 pp. 

Julian, F. and M. Beeson. 1998. Estimates of mammal, turtle and bird mortality for two California gillnet 

fisheries: 1990-1995. Fishery Bulletin 96:271-284. 

Leatherwood, J. S., and M. E. Dahlheim. 1978. Worldwide distribution of pilot whales and killer whales. 

Naval Ocean Systems Center, Tech. Rep. 443:1-39. 

Leatherwood, S., C. O. Matkin, J. D. Hall, and G. M. Ellis. 1990. Killer whales, Orcinus orca, 

photo_identified in Prince William Sound, Alaska 1976 to 1987. Can. Field Naturalist 

104:362_371. 

Mitchell, E. D. 1975. Report on the meeting on small cetaceans, Montreal, April 1-11, 1974. J. Fish. Res. 

Board Canada, 32:914-916. 

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(ed.), The Whale Problem - A Status Report. Harvard University Press, Cambridge, MA. 

Sosa-Nishizaki, O., R. De la Rosa-Pacheco, R. Castro-Longoria, M. Grijalva Chon, and J. De la Rosa 

Velez. 1993. Estudio biologico pesquero del pez (Xiphias gladius) y otras especies de picudos 

(marlins y pez vela). Rep. Int. CICESE, CTECT9306. 

Yano, K. and M. E. Dahlheim. 1995. Killer whale, Orcinus orca, depredation on longline catches of 

bottomfish in the southeastern Bering Sea and adjacent waters. Fishery Bulletin 93:355-372. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the 

GAMMS Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. 

Memo. NMFS-OPR-12. 93 pp. 

130
Revised 10/30/2007 

KILLER WHALE (Orcinus orca): 

Eastern North Pacific Southern Resident Stock

STOCK DEFINITION AND GEOGRAPHIC RANGE

 Killer whales have been observed in all oceans 

and seas of the world (Leatherwood and Dahlheim 1978). 

Although reported from tropical and offshore waters, killer 

whales prefer the colder waters of both hemispheres, with 

greatest abundances found within 800 km of major 

continents (Mitchell 1975). Along the west coast of North 

America, killer whales occur along the entire Alaskan 

coast (Braham and Dahlheim 1982), in British Columbia 

and Washington inland waterways (Bigg et al. 1990), and 

along the outer coasts of Washington, Oregon, and 

California (Green et al. 1992; Barlow 1995, 1997; Forney 

et al. 1995). Seasonal and year-round occurrence has been 

noted for killer whales throughout Alaska (Braham and 

Dahlheim 1982) and in the intracoastal waterways of 

British Columbia and Washington State, where pods have 

been labeled as ‘resident,’ ‘transient,’ and ‘offshore’ (Bigg 

et al. 1990, Ford et al. 1994) based on aspects of 

morphology, ecology, genetics, and behavior (Ford and 

Fisher 1982, Baird and Stacey 1988, Baird et al. 1992, 

Hoelzel et al. 1998). Through examination of photographs 

of recognizable individuals and pods, movements of 

whales between geographical areas have been documented. 

For example, whales identified in Prince William 

Sound have been observed near Kodiak Island (Matkin 

et al. 1999) and whales identified in Southeast Alaska 

have been observed in Prince William Sound, British 

Columbia, and Puget Sound (Leatherwood et al. 1990, 

Dahlheim et al. 1997). 

 Studies on mtDNA restriction patterns provide evidence that the ‘resident’ and ‘transient’ types are 

genetically distinct (Stevens et al. 1989, Hoelzel 1991, Hoelzel and Dover 1991, Hoelzel et al. 1998). Analysis of 

73 samples collected from eastern North Pacific killer whales from California to Alaska has demonstrated 

significant genetic differences among ‘transient’ whales from California through Alaska, ‘resident’ whales from the 

inland waters of Washington, and ‘resident’ whales ranging from British Columbia to the Aleutian Islands and 

Bering Sea (Hoelzel et al. 1998). However, low genetic diversity throughout this specie’s world-wide distribution 

has hampered efforts to clarify its taxonomy. At an international symposium in cetacean systematics in May 2004, a 

workshop was held to review the taxonomy of killer whales. A majority of invited experts felt that the Residentand Transient-type whales in the eastern North Pacific probably merited species or subspecies status (Reeves et al. 

2004). 

Most sightings of the Eastern North Pacific Southern Resident stock of killer whales have occurred in the 

summer in inland waters of Washington and southern British Columbia. However, pods belonging to this stock 

have also been sighted in coastal waters off southern Vancouver Island and Washington (Bigg et al. 1990, Ford et al. 

2000, NWFSC unpubl. data). The complete winter range of this stock is uncertain. Of the three pods comprising 

this stock, one (J1) is commonly sighted in inshore waters in winter, while the other two (K1 and L1) apparently 

spend more time offshore (Ford et al. 2000). These latter two pods have been sighted as far south as Monterey Bay 

and central California in recent years (N. Black, pers. comm., K. Balcomb, pers. comm.) They sometimes have also 

been seen entering the inland waters of Vancouver Island from the north–through Johnstone Strait–in the spring 

(Ford et al. 2000), suggesting that they may spend time along the entire outer coast of Vancouver Island during the 

winter. In May 2003, these pods were sighted off the northern end of the Queen Charlotte Islands, the furthest north 

they had ever previously been documented (J. Ford, pers. comm.). 

 Based on data regarding association patterns, acoustics, movements, genetic differences and potential 

fishery interactions, five killer whale stocks are recognized within the Pacific U.S. EEZ: 1) the Eastern North Pacific 

Northern Resident stock - occurring from British Columbia through Alaska, 2) the Eastern North Pacific Southern 

Figure 1. Approximate April-October distribution 

of the Eastern North Pacific Southern Resident killer 

whale stock (shaded area) and range of sightings 

(dotted line).

Washington

Oregon

Vancouver

Island

Queen 

Charlotte

Islands

California

British Columbia

130°W

130°W

40°N 40°N

50°N 50°N

131
Resident stock - occurring mainly within the inland waters of Washington State and southern British Columbia (see 

Fig. 1), 3) the Eastern North Pacific Transient stock - occurring from Alaska through California, 4) the Eastern 

North Pacific Offshore stock - occurring from Southeast Alaska through California, and 5) the Hawaiian stock. The 

Stock Assessment Reports for the Alaska Region contain information concerning the Eastern North Pacific Northern 

Resident and Eastern North Pacific Transient stocks. 

POPULATION SIZE

 The Eastern North Pacific Southern Resident stock is a trans-boundary stock including killer whales in 

inland Washington and southern British Columbia waters. Photo-identification of individual whales through the 

years has resulted in a substantial understanding of this stock’s structure, behaviors, and movements. In 1993, the 

three pods comprising this stock totaled 96 killer whales (Ford et al. 1994). The population increased to 99 whales 

in 1995, then declined to 79 whales in 2001, and most recently numbered 89 whales in 2006. (Fig. 2; Ford et al. 

2000; Center for Whale Research, unpubl. data). The 2001-2005 counts included a whale born in 1999 (L-98) that 

was listed as missing during the annual census in May and June 2001 but was subsequently discovered alone in an 

inlet off the west coast of Vancouver Island (J. Ford, pers. comm.). L-98 remained separate from L pod until 10 

March 2006 when he died due to injuries associated with a vessel interaction in Nootka Sound. L-98 has been 

subtracted from the official 2006 population census . In addition, four whales that have not been observed during 

the fall 2006 surveys will not be confirmed as missing from the population until the official census is completed in 

May/June 2007 (Center for Whale Research, unpubl. data). 

Minimum Population Estimate

 The abundance estimate for this stock of killer whales is a direct count of individually identifiable animals. 

It is thought that the entire population is censused every year. This estimate therefore serves as both a best estimate 

of abundance and a minimum estimate of abundance. Thus, the minimum population estimate (NMIN) for the 

Eastern North Pacific Southern Resident stock of killer whales is 89 animals. 

Current Population Trend

 During the live-capture fishery 

that existed from 1967 to 1973, it is 

estimated that 47 killer whales, mostly 

immature, were taken out of this stock 

(Ford et al. 1994). The first complete 

census of this stock occurred in 1974. 

Between 1974 and 1993 the Southern 

Resident stock increased approximately 

35%, from 71 to 96 individuals (Ford et 

al. 1994). This represents a net annual 

growth rate of 1.8% during those years. 

Since 1995, the population declined to 79 

whales before increasing from 2002-2006 

to a total of 89 whales (Ford et al. 2000; 

Center for Whale Research, unpubl. 

data). 

50

60

70

80

90

100

19741976197819801982198419861988199019921994199619982000200220042006

Year

Total population

Figure 2. Population of Eastern North Pacific Southern Resident 

stock of killer whales, 1974-2006. Each year’s count includes animals 

first seen and first missed; a whale is considered first missed the year 

after it was last seen alive (Ford et al. 2000; Center for Whale 

Research, unpubl. data). CURRENT AND MAXIMUM NET 

PRODUCTIVITY RATES

 A reliable estimate of the maximum net productivity rate is currently unavailable for this stock of killer 

whales. Studies of ‘resident’ killer whale pods in British Columbia and Washington waters resulted in estimated 

population growth rates of 2.92% and 2.54% over the period from 1973 to 1987 (Olesiuk et al. 1990, Brault and 

Caswell 1993). For southern resident killer whales, estimates of the population growth rate have been made during 

the three periods when the population has been documented increasing since monitoring began in 1974. From 1974 

to 1980 the population increased at a rate of 2.6%/year, 2.3%/year from 1985 to 1996, and 2.5%/year from 2002 to 

2003 (Krahn et al. 2004). However, a population increases at the maximum growth rate (RMAX) only when the 

population is at extremely low levels; thus, any of these estimates may be an underestimate of RMAX. Hence, until 

additional data become available, it is recommended that the cetacean maximum theoretical net productivity rate 

(RMAX) of 4% be employed for this stock (Wade and Angliss 1997). 

132
POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size ( 

89) times one-half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.1 (for 

an endangered stock, Wade and Angliss 1997), resulting in a PBR of 0.18 whales per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fisheries Information

 NMFS observers have monitored the northern Washington marine set gillnet fishery since 1988 (Gearin et 

al. 1994, 2000; P. Gearin, unpubl. data). Observer coverage ranged from approximately 40 to 83% in the entire 

fishery (coastal + inland waters) between 1998 and 2002. There was no observer coverage in this fishery from 

1999-2003. However, the total fishing effort was 4, 46, 4.5 and 7 net days (respectively) in those years, it occurred 

only in inland waters, and no killer whale takes were reported. No killer whale mortalities have been recorded in 

this fishery since the inception of the observer program. 

 In 1993, as a pilot for future observer programs, NMFS in conjunction with the Washington Department of 

Fish and Wildlife (WDFW) monitored all non-treaty components of the Washington Puget Sound Region salmon 

gillnet fishery (Pierce et al. 1994). Observer coverage was 1.3% overall, ranging from 0.9% to 7.3% for the various 

components of the fishery. Encounters (whales within 10 m of a net) with killer whales were reported, but not 

quantified, though no entanglements occurred. 

 In 1994, NMFS and WDFW conducted an observer program during the Puget Sound non-treaty chum 

salmon gillnet fishery (areas 10/11 and 12/12B). A total of 230 sets were observed during 54 boat trips, representing 

approximately 11% observer coverage of the 500 fishing boat trips comprising the total effort in this fishery, as 

estimated from fish ticket landings (Erstad et al. 1996). No interactions with killer whales were observed during this 

fishery. The Puget Sound treaty chum salmon gillnet fishery in Hood Canal (areas 12, 12B, and 12C) and the Puget 

Sound treaty sockeye/chum gillnet fishery in the Strait of Juan de Fuca (areas 4B, 5, and 6C) were also monitored in 

1994 at 2.2% (based on % of total catch observed) and approximately 7.5% (based on % of observed trips to total 

landings) observer coverage, respectively (NWIFC 1995). No interactions resulting in killer whale mortalities were 

reported in either treaty salmon gillnet fishery. 

 Also in 1994, NMFS, WDFW, and the Tribes conducted an observer program to examine seabird and 

marine mammal interactions with the Puget Sound treaty and non-treaty sockeye salmon gillnet fishery (areas 7 and 

7A). During this fishery, observers monitored 2,205 sets, representing approximately 7% of the estimated number 

of sets in the fishery (Pierce et al. 1996). Killer whales were observed within 10 m of the gear during 10 observed 

sets (32 animals in all), though none were observed to have been entangled. 

 Killer whale takes in the Washington Puget Sound Region salmon drift gillnet fishery are unlikely to have 

increased since the fishery was last observed in 1994, due to reductions in the number of participating vessels and 

available fishing time (see details in Appendix 1). Fishing effort and catch have declined throughout all salmon 

fisheries in the region due to management efforts to recover ESA-listed salmonids. 

 An additional source of information on the number of killer whales killed or injured incidental to 

commercial fishery operations is the self-reported fisheries information required of vessel operators by the MMPA. 

During the period between 1994 and 2004, there were no fisher self-reports of killer whale mortalities from any 

fisheries operating within the range of this stock. However, because logbook records (fisher self-reports required 

during 1990-94) are most likely negatively biased (Credle et al. 1994), these are considered to be minimum 

estimates. Logbook data are available for part of 1989-1994, after which incidental mortality reporting requirements 

were modified. Under the new system, logbooks are no longer required; instead, fishers provide self-reports. Data 

for the 1994-1995 phase-in period is fragmentary. After 1995, the level of reporting dropped dramatically, such that 

the records are considered incomplete and estimates of mortality based on them represent minimums (see Appendix 

7 in Angliss and Lodge 2002 for details). 

 Due to a lack of observer programs, there are few data concerning the mortality of marine mammals 

incidental to Canadian commercial fisheries. Since 1990, there have been no reported fishery-related strandings of 

killer whales in Canadian waters. However, in 1994 one killer whale was reported to have contacted a salmon 

gillnet but did not entangle (Guenther et al. 1995). Data regarding the level of killer whale mortality related to 

commercial fisheries in Canadian waters are not available, though the mortality level is thought to be minimal. 

 During this decade there have been no reported takes from this stock incidental to commercial fishing 

operations (D. Ellifrit, pers. comm.), no reports of interactions between killer whales and longline operations (as 

occurs in Alaskan waters; see Yano and Dahlheim 1995), no reports of stranded animals with net marks, and no 

photographs of individual whales carrying fishing gear. The total fishery mortality and serious injury for this stock 

is zero. 

133
Other Mortality

 According to Northwest Marine Mammal Stranding Network records, maintained by the NMFS Northwest 

Region, no human-caused killer whale mortalities or serious injuries were reported from non-fisheries sources in 

1998-2004. There was documentation of a whale-boat collision in Haro Strait in 2005 which resulted in a minor 

injury to a whale. In 2006, whale L98 was killed during a vessel interaction. It is important to note that L98 had 

become habituated to regularly interacting with vessels during its isolation in Nootka Sound. The annual level of 

human-caused mortality for this stock over the past five years is 0.2 animals per year (reflecting the vessel strike 

mortality of animal L98 in 2006). 

STATUS OF STOCK

 On November 15, 2005 NMFS listed Southern Resident killer whales as endangered under the ESA. Total 

annual fishery mortality and serious injury for this stock (0) is not known to exceed 10% of the calculated PBR 

(0.018) and, therefore, appears to be insignificant and approaching zero mortality and serious injury rate. The 

estimated annual level of human-caused mortality and serious injury of 0.2 animals per year exceeds the PBR (0.18). 

Southern Resident killer whales are formally listed as “endangered” under the ESA and consequently the stock is 

automatically considered as a “depleted” and “strategic” stock under the MMPA. 

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136
Revised 10/30/2007 

SHORT-FINNED PILOT WHALE (Globicephala macrorhynchus): 

California/Oregon/Washington Stock 

STOCK DEFINITION AND 

GEOGRAPHIC RANGE

 Short-finned pilot whales 

were once commonly seen off 

Southern California, with an 

apparently resident population around 

Santa Catalina Island, as well as 

seasonal migrants (Dohl et al. 1980). 

After a strong El Niño event in 1982-

83, short-finned pilot whales virtually 

disappeared from this region, and 

despite increased survey effort along 

the entire U.S. west coast, few 

sightings were made from 1984-1992 

(Jones and Szczepaniak 1992; Barlow 

1997; Carretta and Forney 1993; 

Shane 1994; Green et al. 1992, 1993). 

In 1993, six groups of short-finned 

pilot whales were again seen off 

California (Carretta et al. 1995; 

Barlow and Gerrodette 1996), and 

mortality in drift gillnets increased 

(Julian and Beeson 1998) but 

sightings remain rare (Barlow 1997). 

Figure 1 summarizes the sighting 

history of short-finned pilot whales 

off the U.S. west coast. Although the 

full geographic range of the 

California, Oregon, and Washington 

population is not known, it may be 

continuous with animals found off 

Baja California, and its individuals are 

morphologically distinct from shortfinned pilot whales found farther south 

in the eastern tropical Pacific (Polisini 

1981). Separate southern and northern 

forms of short-finned pilot whales have 

also been documented for the western 

North Pacific (Kasuya et al. 1988; Wada 1988; Miyazaki and Amano 1994). For the Marine Mammal 

Protection Act (MMPA) stock assessment reports, short-finned pilot whales within the Pacific U.S. 

Exclusive Economic Zone are divided into two discrete, non-contiguous areas: 1) waters off California, 

Oregon and Washington (this report), and 2) Hawaiian waters. 

OREGON

WASHINGTON

CALIFORNIA

POPULATION SIZE

 Only one group of pilot whales (numbering approximately 7 animals) was seen during the two 

most recent ship surveys conducted off California, Oregon, and Washington in 2001 and 2005 (Barlow 

2003; Forney 2007). All animals were seen during the 2005 survey. The abundance of short-finned pilot 

whales in this region appears to be variable and influenced by prevailing oceanographic conditions, as with 

other odontocete species (Forney 1997, Forney and Barlow 1998). Because animals may spend time 

Figure 1. Short-finned pilot whale sightings made 

during aerial and shipboard surveys conducted off 

California, Oregon, and Washington, 1991-2005. See 

Appendix 2 for data sources and information on timing 

and location of survey effort. Dashed line represents 

the U.S. EEZ, thin lines indicate completed transect 

effort of all surveys combined. 

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

45°0'0"N

40°0'0"N

137
outside the U.S. Exclusive Economic Zone as oceanographic conditions change, a multi-year average 

abundance estimate is the most appropriate for management within U.S. waters. The 2001-2005 

unweighted average abundance estimate for California, Oregon and Washington waters based on the two 

ship surveys is 245 (CV= 0.97) short-finned pilot whales (Barlow 2003; Forney 2007). 

Minimum Population Estimate

 The log-normal 20th percentile of the 2001-2005 unweighted average abundance estimate is 123 

short-finned pilot whales. 

Current Population Trend

 Approximately nine years after the virtual disappearance of short-finned pilot whales following 

the 1982-83 El Niño, they appear to have returned to California waters, as indicated by an increase in 

sighting records as well as incidental fishery mortality (Barlow and Gerrodette 1996; Carretta et al. 1995; 

Julian and Beeson 1998). However, this cannot be considered a true growth in the population, because it 

merely reflects large-scale, long-term movements of this species in response to changing oceanographic 

conditions. It is not known where the animals went after the 82-83 El Niño, or where the recently observed 

animals came from. Until the range of this population and the movements of animals in relation to 

environmental conditions are better documented, no inferences can be drawn regarding trends in abundance 

of short-finned pilot whales off California, Oregon and Washington. 

 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No information on current or maximum net productivity rates is available for short-finned pilot 

whales off California, Oregon and Washington. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum 

population size (123) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a 

recovery factor of 0.40 (for a species of unknown status with a mortality rate CV>0.80; Wade and Angliss 

1997), resulting in a PBR of 0.98 short-finned pilot whales per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

 A summary of known fishery mortality and injury for this stock of short-finned pilot whale is 

shown in Table 1. More detailed information on these fisheries is provided in Appendix 1. Mortality 

estimates for the California drift gillnet fishery are included for the five most recent years of monitoring, 

2000-2004 (Carretta and Chivers 2004, Carretta et al. 2005a, 2005b). After the 1997 implementation of a 

Take Reduction Plan, which included skipper education workshops and required the use of pingers and 

minimum 6-fathom extenders, overall cetacean entanglement rates in the drift gillnet fishery dropped 

considerably (Barlow and Cameron 2003). However, because of interannual variability in entanglement 

rates and the relative rarity of short-finned pilot whale entanglements, additional years of data will be 

required to fully evaluate the effectiveness of pingers for reducing mortality of this particular species. 

There have been 11 pilot whale mortalities observed in this fishery since 1990. In 1993, there were 8 

mortalities observed, and one each in 1990, 1992, 1997 (in an unpingered net) and 2003. Mean annual 

takes in Table 1 are based on 2000-2004 data. This results in an average estimate of 1.0 (CV=1.00) shortfinned pilot whales taken annually. 

 Drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of Baja 

California, Mexico and may take animals from this population. Quantitative data are available only for the 

Mexican swordfish drift gillnet fishery, which uses vessels, gear, and operational procedures similar to 

those in the U.S. drift gillnet fishery, although nets may be up to 4.5 km long (Holts and Sosa-Nishizaki 

1998). The fleet increased from two vessels in 1986 to 31 vessels in 1993 (Holts and Sosa-Nishizaki 1998). 

The total number of sets in this fishery in 1992 can be estimated from data provided by these authors to be 

approximately 2700, with an observed rate of marine mammal bycatch of 0.13 animals per set (10 marine 

mammals in 77 observed sets; Sosa-Nishizaki et al. 1993). This overall mortality rate is similar to that 

observed in California driftnet fisheries during 1990-95 (0.14 marine mammals per set; Julian and Beeson, 

1998), but species-specific information is not available for the Mexican fisheries. Previous efforts to 

convert the Mexican swordfish driftnet fishery to a longline fishery have resulted in a mixed-fishery, with 

138
20 vessels alternately using longlines or driftnets, 23 using driftnets only, 22 using longlines only, and 

seven with unknown gear type (Berdegué 2002). 

 Historically, short-finned pilot whales were also killed in squid purse seine operations off 

Southern California (Miller et al. 1983; Heyning et al. 1994), but these mortalities occurred when pilot 

whales were still common in the region. An observer program in the squid purse seine fishery was initiated 

in 2004 and a total of 193 sets have been observed through 2006 without a pilot whale interaction. 

Observer coverage in this fishery has been less than 10% of all fishing effort. 

 

Table 1. Summary of available information on the incidental mortality and injury of short-finned pilot 

whales (California/ Oregon/Washington Stock) in commercial fisheries that might take this species. All 

observed entanglements of pilot whales resulted in the death of the animal. Coefficients of variation for 

mortality estimates are provided in parentheses; n/a = not available. Mean annual takes are based on 2000-

2004 data unless noted otherwise. 

Fishery Name Data Type

Year(s) 

Percent 

Observer 

Coverage

Observed 

Mortality

Estimated Annual 

Mortality

Mean 

Annual Takes 

(CV in 

parentheses)

CA/OR thresher 

shark/swordfish drift gillnet 

fishery

observer 

2000 

2001 

2002 

2003 

2004

22.9% 

20.4% 

22.0% 

20.0% 

20.6%

0 

0 

0 

1 

0

0 

0 

0 

5 (1.00) 

0

1.0 (1.00)

Market squid purse seine 

fishery observer 2004-2006 <10% 0 0 0 

Minimum total annual takes 1.0 (1.00)

STATUS OF STOCK

 The status of short-finned pilot whales off California, Oregon and Washington in relation to OSP 

is unknown. They have declined in abundance in the Southern California Bight, likely a result of a change 

in their distribution since the 1982-83 El Niño, but the nature of these changes and potential habitat issues 

are not adequately understood. Short-finned pilot whales are not listed as "threatened" or "endangered" 

under the Endangered Species Act nor as "depleted" under the MMPA. The average annual human-caused 

mortality from 2000-2004 is one animal, which is exceeds the PBR (0.98), and therefore they are classified 

as a "strategic" stock under the MMPA. 

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60. 

Wada, S. 1988. Genetic differentiation between forms of short-finned pilot whales off the Pacific coast of 

Japan. Sci. Rep. Whales Res. Inst. 39:91-101. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the 

GAMMS Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. 

Memo. NMFS-OPR-12. 93 pp. 

141
Revised 10/30/2007 

BAIRD'S BEAKED WHALE (Berardius bairdii): 

California/Oregon/Washington Stock 

 

STOCK DEFINITION AND 

GEOGRAPHIC RANGE

 Baird's beaked whales are 

distributed throughout deep waters 

and along the continental slopes of 

the North Pacific Ocean (Balcomb 

1989). They have been harvested 

and studied in Japanese waters, but 

little is known about this species 

elsewhere (Balcomb 1989). Along 

the U.S. west coast, Baird's beaked 

whales have been seen primarily 

along the continental slope (Figure 

1) from late spring to early fall. 

They have been seen less frequently 

and are presumed to be farther 

offshore during the colder water 

months of November through April. 

For the Marine Mammal Protection 

Act (MMPA) stock assessment 

reports, Baird's beaked whales 

within the Pacific U.S. Exclusive 

Economic Zone are divided into two 

discrete, non-contiguous areas: 1) 

waters off California, Oregon and 

Washington (this report), and 2) 

Alaskan waters. 

OREGON

WASHINGTON

CALIFORNIA

POPULATION SIZE

Two summer/fall shipboard surveys 

were conducted within 300 nmi of 

the coasts of California, Oregon and 

Washington in 2001 (Barlow 2003) and 

2005 (Forney 2007). Because the 

distribution of Baird’s beaked whale 

varies and animals probably spend time 

outside the U.S. Exclusive Economic 

Zone, a multi-year average abundance 

estimate is the most appropriate for 

management within U.S. waters. The 2001-2005 geometric mean abundance estimate for California, 

Oregon and Washington waters based on the above two ship surveys is 313 (CV=0.55) Baird’s beaked 

whales (Barlow 1997; Forney 2007). This abundance estimate includes correction factors for the 

proportion of animals missed (g(0) = 0.90 for groups of 1-3 animals, g(0)=1.0 for larger groups), which are 

similar to the estimate of g(0)=0.96 calculated more recently (Barlow 1999) based on dive-interval studies. 

 

Minimum Population Estimate

 The log-normal 20th percentile of the 2001-2005 weighted average abundance estimate is 203 

Baird’s beaked whales. 

Figure 1. Baird’s beaked whale sightings based on 

aerial and shipboard surveys off California, Oregon 

and Washington, 1991-2005 (see Appendix 2 for 

data sources and information on timing and location 

of survey effort). Dashed line represents the U.S. 

EEZ, thin lines indicate completed transect effort of 

all surveys combined. 

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

45°0'0"N

40°0'0"N

142
Current Population Trend

 Due to the rarity of sightings of this species on surveys along the U.S. West coast, no information 

exists regarding trends in abundance of this population. Future studies of trends must take the apparent 

seasonality of the distribution of Baird's beaked whales into account. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No information on current or maximum net productivity rates is available for this species. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum 

population size (203) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a 

recovery factor of 0.50 (for a species of unknown status with no fishery mortality; Wade and Angliss 

1997), resulting in a PBR of 2.0 Baird’s beaked whales per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

 A summary of recent fishery mortality and injury for Baird’s beaked whales in this region is 

shown in Table 1. More detailed information on these fisheries is provided in Appendix 1. Mortality 

estimates for the California drift gillnet fishery are included for the five most recent years of monitoring, 

2000-2004 (Carretta and Chivers 2004, Carretta et al. 2005a, 2005b). After the 1997 implementation of a 

Take Reduction Plan, which included skipper education workshops and required the use of pingers and 

minimum 6-fathom extenders, overall cetacean entanglement rates in the drift gillnet fishery dropped 

considerably (Barlow and Cameron 2003). However, because of interannual variability in entanglement 

rates and the relative rarity of Baird’s beaked whale entanglements, additional years of data will be required 

to fully evaluate the effectiveness of pingers for reducing mortality of this particular species. Mean annual 

takes in Table 1 are based on 2000-2004 data. This results in an average estimated annual mortality of zero 

Baird’s beaked whales. One Baird’s beaked whale was taken in the drift gillnet fishery in 1994. 

Table 1. Summary of available information on the incidental mortality and injury of Baird's beaked whales 

(California/ Oregon/Washington Stock) in commercial fisheries that might take this species. The single 

observed entanglement resulted in the death of the animal. Coefficients of variation for mortality estimates 

are provided in parentheses. Mean annual takes are based on 2000-2004 data unless noted otherwise. 

Fishery Name Data Type

Year(s) 

Percent 

Observer 

Coverage

Observed

Mortality

Estimated Annual 

Mortality

Mean 

Annual Takes 

(CV in 

parentheses) 

CA/OR thresher 

shark/swordfish drift 

gillnet fishery observer 

2000 

2001 

2002 

2003 

2004 

22.9% 

20.4% 

22.1% 

20.2% 

20.6% 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0 

Minimum total annual takes 0

Drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of Baja 

California, Mexico and may take animals from this population. Quantitative data are available only for the 

Mexican swordfish drift gillnet fishery, which uses vessels, gear, and operational procedures similar to 

those in the U.S. drift gillnet fishery, although nets may be up to 4.5 km long (Holts and Sosa-Nishizaki 

1998). The fleet increased from two vessels in 1986 to 31 vessels in 1993 (Holts and Sosa-Nishizaki 1998). 

The total number of sets in this fishery in 1992 can be estimated from data provided by these authors to be 

approximately 2700, with an observed rate of marine mammal bycatch of 0.13 animals per set (10 marine 

mammals in 77 observed sets; Sosa-Nishizaki et al. 1993). This overall mortality rate is similar to that 

observed in California driftnet fisheries during 1990-95 (0.14 marine mammals per set; Julian and Beeson, 

1998), but species-specific information is not available for the Mexican fisheries. Previous efforts to 

convert the Mexican swordfish driftnet fishery to a longline fishery have resulted in a mixed-fishery, with 

143
20 vessels alternately using longlines or driftnets, 23 using driftnets only, 22 using longlines only, and 

seven with unknown gear type (Berdegué 2002). 

Other mortality

 California coastal whaling operations killed 15 Baird's beaked whales between 1956 and 1970, 

and 29 additional Baird's beaked whales were taken by whalers in British Columbian waters (Rice 1974). 

One Baird’s beaked whale stranded in Washington state in 2003 and the cause of death was attributed to a 

ship strike. 

 Additional, unknown levels of injuries and mortalities of Baird’s beaked whales may occur as a 

result of anthropogenic sound, such as military sonars (U.S. Dept. of Commerce and Secretary of the Navy 

2001) or other commercial and scientific activities involving the use of air guns. Such injuries or 

mortalities would rarely be documented, due to the remote nature of many of these activities and the low 

probability that an injured or dead beaked whale would strand. 

STATUS OF STOCK

 The status of Baird's beaked whales in California, Oregon and Washington waters relative to OSP 

is not known, and there are insufficient data to evaluate trends in abundance. No habitat issues are known 

to be of concern for this species, but in recent years questions have been raised regarding potential effects 

of human-made sounds on deep-diving cetacean species, such as Baird’s beaked whales (Richardson et al. 

1995). In particular, active sonar has been implicated in the mass stranding of beaked whales in the 

Mediterranean Sea (Frantzis 1998) and more recently in the Caribbean (U.S. Dept. of Commerce and 

Secretary of the Navy 2001). They are not listed as "threatened" or "endangered" under the Endangered 

Species Act nor as "depleted" under the MMPA. Including the one animal that died as the result of a ship 

strike in 2003, the average annual human-caused mortality in 2000-2004 is 0.2 animals/year. Because 

recent fishery and human-caused mortality is less than the PBR (2.0), Baird’s beaked whales are not 

classified as a "strategic" stock under the MMPA. The total fishery mortality and serious injury for this 

stock is zero and can be considered to be insignificant and approaching zero. 

REFERENCES

Balcomb, K. C., III. 1989. Baird's beaked whale Berardius bairdii Stejneger, 1883: Arnoux's beaked 

whale Berardius arnuxii Duvernoy, 1851. In: Ridgway, S. H. and Harrison, R. (eds.), Handbook 

of Marine Mammals, Vol. 4., p. 261-288. Academic Press Limited. 

Barlow, J. 1997. Preliminary estimates of cetacean abundance off California, Oregon and Washington 

based on a 1996 ship survey and comparisons of passing and closing modes. Administrative 

Report LJ-97-11, Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. 

Box 271, La Jolla, CA 92038. 25p. 

Barlow, J. 1999. Trackline detection probability for long-diving whales. p. 209-224 In: G. W. Garner, S. 

C. Amstrup, J. L. Laake, B. F. J. Manly, L. L. McDonald, and D. G. Robertson (eds.) Marine 

Mammal Survey and Assessment Methods. A. A. Balkema, Rotterdam. 287 pp. 

Barlow, J. and G.A. Cameron. 2003. Field experiments show that acoustic pingers reduce marine mammal 

bycatch in the California drift gillnet fishery. Marine Mammal Science 19(2):265-283. 

Barlow, J. and T. Gerrodette. 1996. Abundance of cetaceans in California waters based on 1991 and 1993 

ship surveys. U.S. Dep. Commer., NOAA Tech. Memo. NMFS-SWFSC-233. 

Barlow, J. 2003. Preliminary estimates of the abundance of cetaceans along the U.S. west coast: 

1991_2001. Southwest Fisheries Science Center Administrative Report LJ_03_03. Available 

from SWFSC, 8604 La Jolla Shores Dr., La Jolla CA 92037. 31p. 

Berdegué, J. 2002. Depredación de las especies pelágicas reservadas a la pesca deportiva y especies en 

peligro de extinción con uso indiscriminado de artes de pesca no selectivas (palangres, FAD's, 

trampas para peces y redes de agallar fijas y a la deriva) por la flota palangrera Mexicana. 

Fundación para la conservación de los picudos. A.C. Mazatlán, Sinaloa, 21 de septiembre. 

Carretta, J.V. and S.J. Chivers. 2004. Preliminary estimates of marine mammal mortality and biological 

sampling of cetaceans in California gillnet fisheries for 2003. Paper SC/56/SM1 presented to the 

IWC Scientific Committee, June 2004 (unpublished). [Available from Southwest Fisheries 

Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 

92037, USA]. 

144
Carretta, J.V., S.J. Chivers, and K. Danil. 2005a. Preliminary estimates of marine mammal bycatch, 

mortality, and biological sampling of cetaceans in California gillnet fisheries for 2004. 

Administrative Report LJ-05-10, available from Southwest Fisheries Science Center, 8604 La 

Jolla Shores Drive, La Jolla, California, 92037. 17 p. 

Carretta, J.V., T. Price, D. Petersen, and R. Read. 2005b. Estimates of marine mammal, sea turtle, and 

seabird mortality in the California drift gillnet fishery for swordfish and thresher shark, 1996-

2002. Marine Fisheries Review 66(2):21-30. 

Frantzis, A. 1998. Does acoustic testing strand whales? Nature 392(5):29. 

Forney, K.A. 2007. Preliminary estimates of cetacean abundance along the U.S. west coast and within 

four National Marine Sanctuaries during 2005. U.S. Department of Commerce, NOAA Technical 

Memorandum NMFS-SWFSC-406. 27p. 

Holts, D. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La Jolla, 

CA 92038. 

Holts, D. and O. Sosa-Nishizaki. 1998. Swordfish, Xiphias gladius, fisheries of the eastern North Pacific 

Ocean. In: I. Barrett, O. Sosa-Nishizaki and N. Bartoo (eds.). Biology and fisheries of swordfish, 

Xiphias gladius. Papers from the International Symposium on Pacific Swordfish, Ensenada 

Mexico, 11-14 December 1994. U.S. Dep. Commer., NOAA Tech. Rep. NMFS 142, 276 p. 

Julian, F. and M. Beeson. 1998. Estimates of mammal, turtle and bird mortality for two California gillnet 

fisheries: 1990-1995. Fish. Bull. 96:271-284. 

Rice, D. W. 1974. Whales and whale research in eastern North Pacific. p. 170-195 In: W. E. Schevill 

(ed.), The Whale Problem - A Status Report. Harvard University Press, Cambridge, MA. 

Richardson, W. J., C. R. Greene, Jr., C. I. Malme, and D. H. Thompson. 1995. Marine Mammals and 

Noise. Academic Press, San Diego. 576 p. 

Sosa-Nishizaki, O., R. De la Rosa-Pacheco, R. Castro-Longoria, M. Grijalva Chon, and J. De la Rosa 

Velez. 1993. Estudio biologico pesquero del pez (Xiphias gladius) y otras especies de picudos 

(marlins y pez vela). Rep. Int. CICESE, CTECT9306. 

U.S. Department of Commerce and Secretary of the Navy. 2001. Joint Interim Report, Bahamas Marine 

Mammal Stranding Event of 15_16 March 2000. Available from NOAA, NMFS, Office of 

Protected Resources, Silver Spring, MD. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the 

GAMMS Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. 

Memo. NMFS-OPR-12. 93 pp. 

145
Revised 10/30/2007 

MESOPLODONT BEAKED WHALES (Mesoplodon spp.): 

 California/Oregon/Washington Stocks 

STOCK DEFINITION AND 

GEOGRAPHIC RANGE

Mesoplodont beaked whales are 

distributed throughout deep waters 

and along the continental slopes of 

the North Pacific Ocean. At least 5 

species in this genus have been 

recorded off the U.S. west coast, 

but due to the rarity of records and 

the difficulty in identifying these 

animals in the field, virtually no 

species-specific information is 

available (Mead 1989). The six 

species known to occur in this 

region are: Blainville's beaked 

whale (M. densirostris), Perrin’s 

beaked whale (M. perrini), Lesser 

beaked whale (M. peruvianus), 

Stejneger's beaked whale (M. 

stejnegeri), Gingko-toothed beaked 

whale (M. gingkodens), and Hubbs' 

beaked whale (M. carlhubbsi). 

Insufficient sighting records exist 

off the U.S. west coast (Figure 1) to 

determine any possible spatial or 

seasonal patterns in the distribution 

of mesoplodont beaked whales. 

 Until methods of 

distinguishing these six species are 

developed, the management unit 

must be defined to include all 

Mesoplodon stocks in this region. 

However, in the future, species-level 

management is desirable, and a high 

priority should be placed on finding 

means to obtain species-specific 

abundance information. For the Marine 

Mammal Protection Act (MMPA) stock 

assessment reports, three Mesoplodon 

stocks are defined: 1) all Mesoplodon

species off California, Oregon and 

Washington (this report), 2) M. stejnegeri in Alaskan waters, and 3) M. densirostris in Hawaiian waters. 

OREGON

WASHINGTON

CALIFORNIA

POPULATION SIZE

 Although mesoplodont beaked whales have been sighted along the U.S. west coast on several line 

transect surveys utilizing both aerial and shipboard platforms, sightings have generally been too rare to 

produce reliable population estimates, and species identification has been problematic. Previous abundance 

estimates have been imprecise and biased downward by an unknown amount because of the large 

proportion of time mesoplodont beaked whales spend submerged, and because the surveys on which they 

were based covered only California waters, and thus could not include animals off Oregon/Washington. 

Furthermore, there were a large number of unidentified beaked whale sightings, which were either 

Figure 1. Mesoplodon beaked whale sightings based 

on aerial and shipboard surveys off California, Oregon 

and Washington, 1991-2005 (see Appendix 2 for data 

sources and information on timing and location of 

survey effort). Key: • = Mesoplodon spp.; filled 

triangles = probable and identified Mesoplodon 

densirostris; + = probable Mesoplodon carlhubbsi.

Dashed line represents the U.S. EEZ, thin lines

indicate completed transect effort of all surveys 

combined. 

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

45°0'0"N

40°0'0"N

146
Mesoplodon sp. or Cuvier's beaked whales (Ziphius cavirostris). Updated analyses are based on 1) 

combining data from two surveys conducted within 300 nmi of the coasts of California, Oregon and 

Washington in 2001 (Barlow 2003) and 2005 (Forney 2007), 2) whenever possible, assigning unidentified 

beaked whale sightings to Mesoplodon spp. or Ziphius cavirostris based on written descriptions, size 

estimates, and ‘most probable identifications’ made by the observers at the time of the sightings, and 3) 

estimating a correction factor for animals missed because they are submerged, based on dive-interval data 

collected for mesoplodont whales in 1993-95 (about 26% of all trackline groups are estimated to be seen). 

Of the 5 sightings of Mesoplodon made during 2001-2005 surveys two were identified to the ‘probable’ 

species level (one Mesoplodon densirostris and one Mesoplodon carlhubbsi; both seen in 2005). The 

current estimate of Blainville’s beaked abundance is based on this one probable sighting, while the Hubb’s 

beaked whale sighting was not recorded during standard survey effort, and thus, there is no estimate of 

abundance. An updated estimate of abundance for unidentified mesoplodont beaked whales is also 

presented, based on 2001-2005 sightings. Because their distribution varies and animals probably spend 

time outside the U.S. Exclusive Economic Zone, a multi-year average abundance estimate is the most 

appropriate for management within U.S. waters. The abundance of Blainville’s beaked whales for 

California, Oregon, and Washington, based on the geometric mean of 2001-2005 surveys is 603 

(CV=1.16). The abundance estimate for mesoplodont beaked whales of unknown species, based on the 

same 2001-2005 surveys is 421 (CV=0.88). The combined estimate of abundance for all species of 

Mesoplodon beaked whales in California, Oregon, and Washington waters out to 300 nmi is 1,024 

(CV=0.77) animals.

Minimum Population Estimate

 The minimum population estimate (defined as the log-normal 20th percentile of the abundance 

estimate) for mesoplodont beaked whales in California, Oregon, and Washington is 576 animals. 

Current Population Trend

 Due to the rarity of sightings of these species on surveys along the U.S. West coast, no 

information exists regarding possible trends in abundance. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No information on current or maximum net productivity rates is available for mesoplodont beaked 

whales. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum 

population size (576) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a 

recovery factor of 0.50 (for a species of unknown status with no known recent fishery mortality; Wade and 

Angliss 1997), resulting in a PBR of 5.7 mesoplodont beaked whales per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

 There have been no recent observed mortalities of mesoplodont beaked whales in the drift gillnet 

fishery for swordfish and thresher shark (Table 1). Between 1990-95, there were a total of five Hubb’s 

beaked whales, one Stegneger’s beaked whale, two unidentified mesoplodont beaked whales, and three 

unidentified beaked whales killed in this fishery (Julian and Beeson 1998). Since 1996, there have been no 

mesoplodont beaked whales observed entangled or killed (Carretta et al. 2005), which coincides with the 

introduction and use of acoustic pingers into this fishery (Barlow and Cameron 2003). A summary of 

recent fishery mortality and injury for mesoplodont beaked whales in this region is shown in Table 1. More 

detailed information on these fisheries is provided in Appendix 1. Mortality estimates for the California 

drift gillnet fishery are included for the five most recent years of monitoring, 2000-2004 ( Carretta and 

Chivers 2004, Carretta et al. 2005a, 2005b). After the 1997 implementation of a Take Reduction Plan, 

which included skipper education workshops and required the use of pingers and minimum 6-fathom 

extenders, overall cetacean entanglement rates in the drift gillnet fishery dropped considerably (Barlow and 

Cameron 2003). However, because of interannual variability in entanglement rates and the relative rarity 

of mesoplodont beaked whale entanglements, additional years of data will be required to fully evaluate the 

effectiveness of pingers for reducing mortality of this group of species. Mean annual takes in Table 1 are 

147
based on 2000-2004 data. This results in an average estimated annual mortality of zero mesoplodont 

beaked whales. 

 Drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of Baja 

California, Mexico and may take animals from this population. Quantitative data are available only for the 

Mexican swordfish drift gillnet fishery, which uses vessels, gear, and operational procedures similar to 

those in the U.S. drift gillnet fishery, although nets may be up to 4.5 km long (Holts and Sosa-Nishizaki 

1998). The fleet increased from two vessels in 1986 to 31 vessels in 1993 (Holts and Sosa-Nishizaki 1998). 

The total number of sets in this fishery in 1992 can be estimated from data provided by these authors to be 

approximately 2700, with an observed rate of marine mammal bycatch of 0.13 animals per set (10 marine 

mammals in 77 observed sets; Sosa-Nishizaki et al. 1993). This overall mortality rate is similar to that 

observed in California driftnet fisheries during 1990-95 (0.14 marine mammals per set; Julian and Beeson, 

1998), but species-specific information is not available for the Mexican fisheries. Previous efforts to 

convert the Mexican swordfish driftnet fishery to a longline fishery have resulted in a mixed-fishery, with 

20 vessels alternately using longlines or driftnets, 23 using driftnets only, 22 using longlines only, and 

seven with unknown gear type (Berdegué 2002). 

 

Table 1. Summary of available information on the incidental mortality and injury of Mesoplodon beaked 

whales (California/Oregon/Washington Stocks) in commercial fisheries that might take these species. 

Mean annual takes are based on 2000-2004 data unless noted otherwise. 

Fishery Name Data Type

Year 

Percent 

Observer 

Coverage

Observed

Mortality

Estimated 

Annual 

Mortality

Mean 

Annual Takes 

(CV in 

parentheses)

CA/OR thresher 

shark/swordfish drift gillnet 

fishery 

observer 

2000 

2001 

2002 

2003 

2004 

22.9% 

20.4% 

22.1% 

20.2% 

20.6% 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0 

Minimum total annual takes of Mesoplodon beaked whales 0 

Other mortality

 Additional, unknown levels of injuries and mortalities of mesoplodont beaked whales may occur 

as a result of anthropogenic sound, such as military sonars (U.S. Dept. of Commerce and Secretary of the 

Navy 2001) or other commercial and scientific activities involving the use of air guns. Such injuries or 

mortalities would rarely be documented, due to the remote nature of many of these activities and the low 

probability that an injured or dead beaked whale would strand. 

STATUS OF STOCKS

 The status of mesoplodont beaked whales in California, Oregon and Washington waters relative to 

OSP is not known, and there are insufficient data to evaluate trends in abundance. No habitat issues are 

known to be of concern for this species, but in recent years questions have been raised regarding potential 

effects of human-made sounds on deep-diving cetacean species, such as mesoplodont beaked whales 

(Richardson et al. 1995). In particular, active sonar has been implicated in the mass stranding of beaked 

whales in the Mediterranean Sea (Frantzis 1998) and more recently in the Bahamas (U.S. Dept. of 

Commerce and Secretary of the Navy 2001).

 None of the six species is listed as "threatened" or "endangered" under the Endangered Species 

Act nor considered "depleted" under the MMPA. Including driftnet mortality only for years after 

implementation of the Take Reduction Plan (1997-98), the average annual human-caused mortality in 

2000-2004 is zero. Because recent mortality is zero, mesoplodont beaked whales are not classified as a 

"strategic" stock under the MMPA, and the total fishery mortality and serious injury for this stock can be 

considered to be insignificant and approaching zero. It is likely that the difficulty in identifying these 

animals in the field will remain a critical obstacle to obtaining species-specific abundance estimates and 

stock assessments in the future. 

148
REFERENCES

Barlow, J. 1997. Preliminary estimates of cetacean abundance off California, Oregon, and Washington 

based on a 1996 ship survey and comparisons of passing and closing modes. Southwest Fisheries 

Science Center Administrative Report. LJ-97-11. 25pp. 

Barlow, J. 1997. Preliminary estimates of cetacean abundance off California, Oregon and Washington 

based on a 1996 ship survey and comparisons of passing and closing modes. Administrative 

Report LJ-97-11, Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. 

Box 271, La Jolla, CA 92038. 25p. 

Barlow, J. and G. A. Cameron. 2003. Field experiments show that acoustic pingers reduce marine mammal 

bycatch in the California drift gillnet fishery. Marine Mammal Science 19(2):265-283. 

Barlow, J. and T. Gerrodette. 1996. Abundance of cetaceans in California waters based on 1991 and 1993 

ship surveys. NOAA Technical Memorandum NMFS, NOAA-TM-NMFS-SWFSC-233. 

Barlow, J. and S. Sexton. 1996. The effect of diving and searching behavior on the probability of 

detecting track-line groups, g0, of long-diving whales during line transect surveys. Administrative 

Report LJ-96-14. Available from NMFS, Southwest Fisheries Science Center, P.O. Box 271, La 

Jolla, California, 92038, USA. 21 p. 

Barlow, J. 2003. Preliminary estimates of the abundance of cetaceans along the U.S. west coast: 

1991_2001. Southwest Fisheries Science Center Administrative Report LJ_03_03. Available 

from SWFSC, 8604 La Jolla Shores Dr., La Jolla CA 92037. 31p. 

Berdegué, J. 2002. Depredación de las especies pelágicas reservadas a la pesca deportiva y especies en 

peligro de extinción con uso indiscriminado de artes de pesca no selectivas (palangres, FAD's, 

trampas para peces y redes de agallar fijas y a la deriva) por la flota palangrera Mexicana. 

Fundación para la conservación de los picudos. A.C. Mazatlán, Sinaloa, 21 de septiembre. 

Carretta, J.V. and S.J. Chivers. 2004. Preliminary estimates of marine mammal mortality and biological 

sampling of cetaceans in California gillnet fisheries for 2003. Paper SC/56/SM1 presented to the 

IWC Scientific Committee, June 2004 (unpublished). [Available from Southwest Fisheries 

Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 

92037, USA]. 

Carretta, J.V., S.J. Chivers, and K. Danil. 2005a. Preliminary estimates of marine mammal bycatch, 

mortality, and biological sampling of cetaceans in California gillnet fisheries for 2004. 

Administrative Report LJ-05-10, available from Southwest Fisheries Science Center, 8604 La 

Jolla Shores Drive, La Jolla, California, 92037. 17 p. 

Carretta, J.V., T. Price, D. Petersen, and R. Read. 2005b. Estimates of marine mammal, sea turtle, and 

seabird mortality in the California drift gillnet fishery for swordfish and thresher shark, 1996-

2002. Marine Fisheries Review 66(2):21-30. 

Frantzis, A. 1998. Does acoustic testing strand whales? Nature 392(5):29. 

Forney, K.A. 2007. Preliminary estimates of cetacean abundance along the U.S. west coast and within 

four National Marine Sanctuaries during 2005. U.S. Department of Commerce, NOAA Technical 

Memorandum NMFS-SWFSC-406. 27p. 

Holts, D. and O. Sosa-Nishizaki. 1998. Swordfish, Xiphias gladius, fisheries of the eastern North Pacific 

Ocean. In: I. Barrett, O. Sosa-Nishizaki and N. Bartoo (eds.). Biology and fisheries of swordfish, 

Xiphias gladius. Papers from the International Symposium on Pacific Swordfish, Ensenada 

Mexico, 11-14 December 1994. U.S. Dep. Commer., NOAA Tech. Rep. NMFS 142, 276 p. 

Julian, F. and M. Beeson. 1998. Estimates of mammal, turtle and bird mortality for two California gillnet 

fisheries: 1990-1995. Fishery Bulletin 96:271-284. 

Mead, J. G. 1989. Beaked whales of the genus Mesoplodon. In: Ridgway, S. H. and Harrison, R. (eds.), 

Handbook of Marine Mammals, Vol. 4., p. 349-430. Academic Press Limited. 

National Marine Fisheries Service, Southwest Fisheries Science Center. Unpublished data. 

Richardson, W. J., C. R. Greene, Jr., C. I. Malme, and D. H. Thompson. 1995. Marine Mammals and 

Noise. Academic Press, San Diego. 576 p. 

Sosa-Nishizaki, O., R. De la Rosa-Pacheco, R. Castro-Longoria, M. Grijalva Chon, and J. De la Rosa 

Velez. 1993. Estudio biologico pesquero del pez (Xiphias gladius) y otras especies de picudos 

(marlins y pez vela). Rep. Int. CICESE, CTECT9306. 

U.S. Department of Commerce and Secretary of the Navy. 2001. Joint Interim Report, Bahamas Marine 

Mammal Stranding Event of 15_16 March 2000. Available from NOAA, NMFS, Office of 

Protected Resources, Silver Spring, MD. 

149
Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the 

GAMMS Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. 

Memo. NMFS-OPR-12. 93 pp. 

150
Revised 10/30/2007 

CUVIER'S BEAKED WHALE (Ziphius cavirostris): 

California/Oregon/Washington Stock 

STOCK DEFINITION AND 

GEOGRAPHIC RANGE

 Cuvier's beaked whales are 

distributed widely throughout deep 

waters of all oceans (Heyning 

1989). Off the U.S. west coast, this 

species is the most commonly 

encountered beaked whale (Figure 

1). No seasonal changes in 

distribution are apparent from 

stranding records, and 

morphological evidence is 

consistent with the existence of a 

single eastern North Pacific 

population from Alaska to Baja 

California, Mexico (Mitchell 1968). 

However, there are currently no 

international agreements for 

cooperative management of this 

species. For the Marine Mammal 

Protection Act (MMPA) stock 

assessment reports, Cuvier's beaked 

whales within the Pacific U.S. 

Exclusive Economic Zone are 

divided into three discrete, noncontiguous areas: 1) waters off 

California, Oregon and Washington 

(this report), 2) Alaskan waters, and 

3) Hawaiian waters. 

OREGON

WASHINGTON

CALIFORNIA

POPULATION SIZE

 Although Cuvier's beaked whales 

have been sighted along the U.S. west coast 

on several line transect surveys utilizing 

both aerial and shipboard platforms, 

sightings have been too rare to produce 

reliable population estimates. Previous 

abundance estimates have been imprecise and biased downward by an unknown amount because of the 

large proportion of time this species spends submerged, and because the ship surveys on which they were 

based covered only California waters, and thus could not observe animals off Oregon/Washington. 

Furthermore, there were a large number of unidentified beaked whale sightings, which were probably either 

Mesoplodon sp. or Cuvier's beaked whales (Ziphius cavirostris). Updated analyses are based on 1) 

combining data from two surveys conducted within 300 nmi of the coasts of California, Oregon and 

Washington in 2001 (Barlow 2003) and 2005 (Forney 2007), 2) whenever possible, assigning unidentified 

beaked whale sightings to Mesoplodon spp. or Ziphius cavirostris based on written descriptions, size 

estimates, and ‘most probable identifications’ made by the observers at the time of the sightings, and 3) 

estimating a correction factor for animals missed because they are submerged, based on dive-interval data 

collected for Cuvier’s beaked whales in 1993-95 (an estimated 13% of all groups are estimated to be seen). 

Because animals probably spend time outside the U.S. Exclusive Economic Zone, a multi-year average 

Figure 1. Cuvier’s beaked whale sightings 

based on aerial and shipboard surveys off 

California, Oregon and Washington, 1991-2005 

(see Appendix 2, for data sources and 

information on timing and location of survey 

effort). Dashed line represents the U.S. EEZ, 

thin lines indicate completed transect effort of all 

surveys combined. 

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

45°0'0"N

40°0'0"N

151
abundance estimate is the most appropriate for management within U.S. waters. The 2001-2005 geometric 

mean abundance estimate for California, Oregon and Washington waters based on the above analyses is 

2,171 (CV= 0.75) Cuvier’s beaked whales. 

Minimum Population Estimate

 Based on the above abundance estimate and CV, the minimum population estimate (defined as the 

log-normal 20th percentile of the abundance estimate) for Cuvier's beaked whales in California, Oregon, 

and Washington is 1,234 animals. 

Current Population Trend

 Due to the rarity of sightings of this species on surveys along the U.S. West coast, no information 

exists regarding trends in abundance of this population. 

 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No information on current or maximum net productivity rates is available for this species. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum 

population size (1,234) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times

a recovery factor of 0.40 (for a species of unknown status with an unknown fishery mortality CV; Wade 

and Angliss 1997), resulting in a PBR of 10 Cuvier’s beaked whales per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

 A summary of recent fishery mortality and injury for Cuvier’s beaked whales in this region is 

shown in Table 1. More detailed information on these fisheries is provided in Appendix 1. Mortality 

estimates for the California drift gillnet fishery are included for the five most recent years of monitoring, 

2000-2004 (Carretta and Chivers 2004, Carretta et al. 2005a, 2005b). After the 1997 implementation of a 

Take Reduction Plan, which included skipper education workshops and required the use of pingers and 

minimum 6-fathom extenders, overall cetacean entanglement rates in the drift gillnet fishery dropped 

considerably (Barlow and Cameron 2003). There have been no Cuvier’s beaked whales observed 

entangled in over 4,000 drift gillnet fishery sets since pingers were first used in this fishery in 1996. Prior to 

1996, there were a total of 21 Cuvier’s beaked whales entangled in approximately 3,300 drift gillnet fishery 

sets: 1992 (six animals), 1993 (three), 1994 (six) and 1995 (six). A dead stranded Cuvier’s beaked whale in 

2001 died as the result of an interaction with an unknown entangling net fishery (NMFS, Northwest 

Regional Office, unpublished stranding data, Brent Norberg, pers. comm.; Jim Rice, Oregon State 

University, pers. comm.). Mean annual takes in Table 1 are based only on 2000-2004 data. This results in 

an average estimated annual mortality of 0.2 Cuvier’s beaked whales. 

 Drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of Baja 

California, Mexico and may take animals from this population. Quantitative data are available only for the 

Mexican swordfish drift gillnet fishery, which uses vessels, gear, and operational procedures similar to 

those in the U.S. drift gillnet fishery, although nets may be up to 4.5 km long (Holts and Sosa-Nishizaki 

1998). The fleet increased from two vessels in 1986 to 31 vessels in 1993 (Holts and Sosa-Nishizaki 1998). 

The total number of sets in this fishery in 1992 can be estimated from data provided by these authors to be 

approximately 2700, with an observed rate of marine mammal bycatch of 0.13 animals per set (10 marine 

mammals in 77 observed sets; Sosa-Nishizaki et al. 1993). This overall mortality rate is similar to that 

observed in California driftnet fisheries during 1990-95 (0.14 marine mammals per set; Julian and Beeson, 

1998), but species-specific information is not available for the Mexican fisheries. Previous efforts to 

convert the Mexican swordfish driftnet fishery to a longline fishery have resulted in a mixed-fishery, with 

20 vessels alternately using longlines or driftnets, 23 using driftnets only, 22 using longlines only, and 

seven with unknown gear type (Berdegué 2002). 

152
Table 1. Summary of available information on the incidental mortality and injury of Cuvier's beaked 

whales (California/ Oregon/Washington Stock) in commercial fisheries that might take this species. Mean 

annual takes are based on 2000-2004 data unless noted otherwise. n/a = not available. 

Fishery Name Data Type

Year(s) 

Percent 

Observer 

Coverage

Observed 

Mortality + 

ReleasedAlive

Estimated Annual 

Mortality / Mortality + 

Entanglements

Mean 

Annual Takes 

(CV in 

parentheses)

CA/OR thresher 

shark/swordfish drift 

gillnet fishery 

observer 

data 

2000 

2001 

2002 

2003 

2004 

22.9% 

20.4% 

22.1% 

20.2% 

20.6% 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0 

Unknown fishery Stranding 2000-2004 n/a 1 ≥1 (n/a) ≥0.2 (n/a) 

Minimum total annual takes ≥0.2 (n/a)

Other mortality

 Additional, unknown levels of injuries and mortalities of Cuvier’s beaked whales may occur as a 

result of anthropogenic sound, such as military sonars (U.S. Dept. of Commerce and Secretary of the Navy 

2001) or other commercial and scientific activities involving the use of air guns. Such injuries or 

mortalities would rarely be documented, due to the remote nature of many of these activities and the low 

probability that an injured or dead beaked whale would strand. 

STATUS OF STOCK

 The status of Cuvier's beaked whales in California, Oregon and Washington waters relative to 

OSP is not known, and there are insufficient data to evaluate trends in abundance. No habitat issues are 

known to be of concern for this species, but in recent years questions have been raised regarding potential 

effects of human-made sounds on deep-diving cetacean species, such as Cuvier’s beaked whales 

(Richardson et al. 1995). In particular, active sonar has been implicated in the mass stranding of beaked 

whales in the Mediterranean Sea (Frantzis 1998) and more recently in the Caribbean (U.S. Dept. of 

Commerce and Secretary of the Navy 2001). They are not listed as "threatened" or "endangered" under the 

Endangered Species Act nor as "depleted" under the MMPA. The average annual human-caused mortality 

in 2000-2004 is 0.2. Because recent human-caused mortality is less than the PBR of 10 animals, Cuvier’s 

beaked whales are not classified as a "strategic" stock under the MMPA. The total fishery mortality and 

serious injury for this stock is less than 10% of the PBR and thus can be considered to be insignificant and 

approaching zero. 

REFERENCES

Barlow, J. 1997. Preliminary estimates of cetacean abundance off California, Oregon and Washington 

based on a 1996 ship survey and comparisons of passing and closing modes. Administrative 

Report LJ-97-11, Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. 

Box 271, La Jolla, CA 92038. 25p. 

Barlow, J. and G. A. Cameron. 2003. Field experiments show that acoustic pingers reduce marine mammal 

bycatch in the California drift gillnet fishery. Marine Mammal Science 19(2):265-283. 

Barlow, J. and T. Gerrodette. 1996. Abundance of cetaceans in California waters based on 1991 and 1993 

ship surveys. NOAA Technical Memorandum NMFS, NOAA-TM-NMFS-SWFSC-233. 

Barlow, J. and S. Sexton. 1996. The effect of diving and searching behavior on the probability of 

detecting track-line groups, g0, of long-diving whales during line transect surveys. Administrative 

Report LJ-96-14. Available from NMFS, Southwest Fisheries Science Center, P.O. Box 271, La 

Jolla, California, 92038, USA. 21 p. 

Barlow, J. 2003. Preliminary estimates of the abundance of cetaceans along the U.S. west coast: 

1991_2001. Southwest Fisheries Science Center Administrative Report LJ_03_03. Available 

from SWFSC, 8604 La Jolla Shores Dr., La Jolla CA 92037. 31p. 

Berdegué, J. 2002. Depredación de las especies pelágicas reservadas a la pesca deportiva y especies en 

peligro de extinción con uso indiscriminado de artes de pesca no selectivas (palangres, FAD's, 

153
trampas para peces y redes de agallar fijas y a la deriva) por la flota palangrera Mexicana. 

Fundación para la conservación de los picudos. A.C. Mazatlán, Sinaloa, 21 de septiembre. 

Carretta, J.V. and S.J. Chivers. 2004. Preliminary estimates of marine mammal mortality and biological 

sampling of cetaceans in California gillnet fisheries for 2003. Paper SC/56/SM1 presented to the 

IWC Scientific Committee, June 2004 (unpublished). [Available from Southwest Fisheries 

Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 

92037, USA]. 

Carretta, J.V., S.J. Chivers, and K. Danil. 2005a. Preliminary estimates of marine mammal bycatch, 

mortality, and biological sampling of cetaceans in California gillnet fisheries for 2004. 

Administrative Report LJ-05-10, available from Southwest Fisheries Science Center, 8604 La 

Jolla Shores Drive, La Jolla, California, 92037. 17 p. 

Carretta, J.V., T. Price, D. Petersen, and R. Read. 2005b. Estimates of marine mammal, sea turtle, and 

seabird mortality in the California drift gillnet fishery for swordfish and thresher shark, 1996-

2002. Marine Fisheries Review 66(2):21-30. 

Frantzis, A. 1998. Does acoustic testing strand whales? Nature 392(5):29. 

Forney, K.A. 2007. Preliminary estimates of cetacean abundance along the U.S. west coast and within 

four National Marine Sanctuaries during 2005. U.S. Department of Commerce, NOAA Technical 

Memorandum NMFS-SWFSC-406. 27p. 

Heyning, J. E. 1989. Cuvier’s beaked whale Ziphius cavirostris G. Cuvier, 1823. pp. 289-308 In:

Ridgway, S. H. and R. Harrison (eds.), Handbook of Marine Mammals, Vol. 4. Academic Press. 

Holts, D. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La Jolla, 

CA 92038. 

Holts, D. and O. Sosa-Nishizaki. 1998. Swordfish, Xiphias gladius, fisheries of the eastern North Pacific 

Ocean. In: I. Barrett, O. Sosa-Nishizaki and N. Bartoo (eds.). Biology and fisheries of swordfish, 

Xiphias gladius. Papers from the International Symposium on Pacific Swordfish, Ensenada 

Mexico, 11-14 December 1994. U.S. Dep. Commer., NOAA Tech. Rep. NMFS 142, 276 p. 

Julian, F. and M. Beeson. 1998. Estimates of mammal, turtle and bird mortality for two California gillnet 

fisheries: 1990-1995. Fish. Bull. 96:271-284. 

Mitchell, E. 1968. Northeast Pacific stranding distribution and seasonality of Cuvier's beaked whale, 

Ziphius cavirostris. Can. J. Zool. 46:265-279. 

Richardson, W. J., C. R. Greene, Jr., C. I. Malme, and D. H. Thompson. 1995. Marine Mammals and 

Noise. Academic Press, San Diego. 576 p. 

Sosa-Nishizaki, O., R. De la Rosa-Pacheco, R. Castro-Longoria, M. Grijalva Chon, and J. De la Rosa 

Velez. 1993. Estudio biologico pesquero del pez (Xiphias gladius) y otras especies de picudos 

(marlins y pez vela). Rep. Int. CICESE, CTECT9306. 

U.S. Department of Commerce and Secretary of the Navy. 2001. Joint Interim Report, Bahamas Marine 

Mammal Stranding Event of 15_16 March 2000. Available from NOAA, NMFS, Office of 

Protected Resources, Silver Spring, MD. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the 

GAMMS Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. 

Memo. NMFS-OPR-12. 93 pp. 

154
Revised 10/30/2007 

PYGMY SPERM WHALE (Kogia breviceps): 

California/Oregon/Washington Stock 

STOCK DEFINITION AND 

GEOGRAPHIC RANGE

 Pygmy sperm whales are 

distributed throughout deep waters and along 

the continental slopes of the North Pacific 

and other ocean basins (Ross 1984; Caldwell 

and Caldwell 1989). Along the U.S. west 

coast, sightings of this species and of 

animals identified only as Kogia sp. have 

been very rare (Figure 1). However, this 

probably reflects their pelagic distribution, 

small body size and cryptic behavior, rather 

than a measure of rarity. Strandings of 

pygmy sperm whales in this region are 

known from California, Oregon and 

Washington (Roest 1970; Caldwell and 

Caldwell 1989; NMFS, Northwest Region, 

unpublished data; NMFS, Southwest 

Region, unpublished data), while strandings 

of dwarf sperm whales (Kogia sima) are rare 

in this region. At-sea sightings in this region 

have all been either of pygmy sperm whales 

or unidentified Kogia sp. Available data are 

insufficient to identify any seasonality in the 

distribution of pygmy sperm whales, or to 

delineate possible stock boundaries. For the 

Marine Mammal Protection Act (MMPA) 

stock assessment reports, pygmy sperm 

whales within the Pacific U.S. Exclusive 

Economic Zone are divided into two 

discrete, non-contiguous areas: 1) waters off 

California, Oregon and Washington (this 

report), and 2) Hawaiian waters. 

OREGON

WASHINGTON

CALIFORNIA

POPULATION SIZE 

Although pygmy sperm whales have 

been sighted along the U.S. west coast on several 

line transect surveys utilizing both aerial and 

shipboard platforms, sightings have been too rare 

to produce reliable population estimates. Previous abundance estimates of 247 (CV = 1.06) pygmy sperm whales 

were based on pooled 1996-2001 ship surveys of California, Oregon, and Washington waters, where there were only 

two sightings (both in 1996) that could be identified to the genus Kogia. (Barlow 2003). Based on previous sighting 

surveys and historical stranding data, it is likely that these sightings were of pygmy sperm whales; K. breviceps. 

The 1996-2001 pooled estimate incorporates a correction factor for animals missed because they are submerged, 

based on dive-interval data collected for Kogia sima in 1993-95 (about 19% of all groups are estimated to be seen). 

Because animals probably spend time outside the U.S. Exclusive Economic Zone, a multi-year average abundance 

estimate is the most appropriate for management within U.S. waters. Because no sightings of pygmy sperm whales 

have been recorded during the two most recent ship surveys conducted in 2001 (Barlow 2003) and 2005 (Forney 

2007), there is no current estimate of abundance available. The lack of recent sightings likely reflects the cryptic 

nature of this species (they are detected almost exclusively in extremely calm sea conditions), rather than an absence 

of animals in the region. 

Figure 1. Kogia sightings based on aerial and shipboard 

surveys off California, Oregon and Washington, 1991-

2005 (see Appendix 2 for data sources and information 

on timing and location of survey effort). Key: ■ = 

Kogia breviceps, ● = Kogia spp. Dashed line represents 

the U.S. EEZ, thin lines indicate completed transect 

effort of all surveys combined. 

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

45°0'0"N

40°0'0"N

155
 

Minimum Population Estimate

 No current information on abundance is available to obtain a minimum population estimate for pygmy 

sperm whales. 

Current Population Trend

 Due to the rarity of sightings of this species on surveys along the U.S. West coast, no information exists 

regarding trends in abundance of this population. 

 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No information on current or maximum net productivity rates is available for this species. 

POTENTIAL BIOLOGICAL REMOVAL

 Because there is no current estimate of minimum abundance, a potential biological removal (PBR) cannot 

be calculated for this stock. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

 A summary of recent fishery mortality and injury for pygmy sperm whales and unidentified Kogia, which 

may have been pygmy sperm whales, is shown in Table 1. More detailed information on the drift gillnet fishery is 

provided in Appendix 1. In the California drift gillnet fishery, no mortality of pygmy sperm whales or unidentified 

Kogia was observed during the most recent five years of monitoring, 2000-2004 (Carretta and Chivers 2004, 

Carretta et al. 2005a, 2005b). One pygmy sperm whale was observed killed in the drift gillnet fishery in 1992 and 

another in 1993. After the 1997 implementation of a Take Reduction Plan, which included skipper education 

workshops and required the use of pingers and minimum 6-fathom extenders, overall cetacean entanglement rates in 

the drift gillnet fishery dropped considerably (Barlow and Cameron 2003). However, because of interannual 

variability in entanglement rates and the rarity of Kogia entanglements, additional years of data will be required to 

fully evaluate the effectiveness of pingers for reducing mortality of pygmy sperm whales. Mean annual takes in 

Table 1 are based on 2000-2004 data. This results in an average estimated annual mortality of zero pygmy sperm 

whales. 

 Drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of Baja California, 

Mexico and may take animals from this population. Quantitative data are available only for the Mexican swordfish 

drift gillnet fishery, which uses vessels, gear, and operational procedures similar to those in the U.S. drift gillnet 

fishery, although nets may be up to 4.5 km long (Holts and Sosa-Nishizaki 1998). The fleet increased from two 

vessels in 1986 to 31 vessels in 1993 (Holts and Sosa-Nishizaki 1998). The total number of sets in this fishery in 

1992 can be estimated from data provided by these authors to be approximately 2700, with an observed rate of 

marine mammal bycatch of 0.13 animals per set (10 marine mammals in 77 observed sets; Sosa-Nishizaki et al. 

1993). This overall mortality rate is similar to that observed in California driftnet fisheries during 1990-95 (0.14 

marine mammals per set; Julian and Beeson, 1998), but species-specific information is not available for the Mexican 

fisheries. Previous efforts to convert the Mexican swordfish driftnet fishery to a longline fishery have resulted in a 

mixed-fishery, with 20 vessels alternately using longlines or driftnets, 23 using driftnets only, 22 using longlines 

only, and seven with unknown gear type (Berdegué 2002). 

Other mortality

 One pygmy sperm whale stranded in California in 2002 with evidence that it died as a result of a shooting 

(positive metal detector scan). This results in an average annual human-caused mortality of 0.2 pygmy sperm 

whales per year. Additional, unknown levels of injuries and mortalities of pygmy sperm whales may occur as a 

result of anthropogenic sound, such as military sonars (U.S. Dept. of Commerce and Secretary of the Navy 2001) or 

other commercial and scientific activities involving the use of air guns. Such injuries or mortalities would rarely be 

documented, due to the remote nature of many of these activities and the low probability that an injured or dead 

pygmy sperm whale would strand. 

STATUS OF STOCK

 The status of pygmy sperm whales in California, Oregon and Washington waters relative to OSP is not 

known, and there are insufficient data to evaluate potential trends in abundance. No habitat issues are known to be 

of concern for this species, but in recent years questions have been raised regarding potential effects of human-made

156
sounds on deep-diving cetacean species, such as pygmy sperm whales (Richardson et al. 1995). In particular, active 

sonar has been implicated in the mass stranding of beaked whales in the Mediterranean Sea (Frantzis 1998) and 

more recently in the Caribbean (U.S. Dept. of Commerce and Secretary of the Navy 2001). They are not listed as 

"threatened" or "endangered" under the Endangered Species Act nor as "depleted" under the MMPA. The average 

annual human-caused mortality for 2000-2004 is 0.2 animals, based on one stranded animal in 2002 that had 

evidence of gunshot wounds. A PBR cannot be calculated for this stock because there have been no sightings of 

pygmy sperm whales from the two most recent ship line transect surveys conducted in 2001 and 2005 (Barlow 2003, 

Forney 2007). The lack of recent sightings is probably due to a combination of rough sea conditions during these 

two cruises and the cryptic nature of this species. Previous estimates of PBR for this stock have ranged between 1 

and 28 pygmy sperm whales (Barlow et al. 1995, Barlow et al. 1997, Forney et al. 2000, Carretta et al. 2003). 

Recent fishery mortality is zero and the total fishery mortality and serious injury for this stock can be considered to 

be insignificant and approaching zero. Given the range of PBRs for this stock in previous years, the lack observed 

fishery mortality, and lack of recent information on population size, pygmy sperm whales are not classified as a 

“strategic” stock under the MMPA.

Table 1. Summary of available information on the incidental mortality and injury of pygmy sperm whales and 

unidentified Kogia sp. (California/Oregon/Washington Stock) in commercial fisheries that might take this species. 

Coefficients of variation for mortality estimates are provided in parentheses. Mean annual takes are based on 2000-

2004 data unless noted otherwise. 

Fishery Name Data Type

Year(s) 

Percent 

Observer 

Coverage

Observed 

Mortality 

K. breviceps 

/Kogia sp.

Estimated Annual 

Mortality of K. 

breviceps/Kogia sp.

Mean 

Annual Takes 

(CV in parentheses)

CA/OR thresher 

shark/swordfish drift gillnet 

fishery 

observer 

data 

2000 

2001 

2002 

2003 

2004 

22.9% 

20.4% 

22.1% 

20.2% 

20.6% 

0 / 0 

0 / 0 

0 / 0 

0 / 0 

0 / 0 

0 / 0 

0 / 0 

0 / 0 

0 / 0 

0 / 0 

0 

Minimum total annual takes 0

REFERENCES 

Barlow, J., R.L. Brownell, Jr., D.P. DeMaster, K.A. Forney, M.S. Lowry, S. Osmeck, T.J. Ragen, R.R. Reeves, and 

R.J. Small. 1995. U.S. Pacific Marine Mammal Stock Assessments. NOAA Technical Memorandum 

NOAA-TM-NMFS-SWFSC-219. 162p. 

Barlow, J. 1997. Preliminary estimates of cetacean abundance off California, Oregon and Washington based on a 

1996 ship survey and comparisons of passing and closing modes. Administrative Report LJ-97-11, 

Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La Jolla, CA 92038. 

25p. 

Barlow, J., K.A. Forney, P.S. Hill, R.L. Brownell, Jr., J.V. Carretta, D.P. DeMaster, F. Julian, M.S. Lowry, T. 

Ragen, and R.R. Reeves. 1997. U.S. Pacific Marine Mammal Stock Assessments: 1996. NOAA 

Technical Memorandum NOAA-TM-NMFS-SWFSC-248. 223p. 

Barlow, J. and G. A. Cameron. 2003. Field experiments show that acoustic pingers reduce marine mammal bycatch 

in the California drift gillnet fishery. Marine Mammal Science 19(2):265-283. 

Barlow, J. and T. Gerrodette. 1996. Abundance of cetaceans in California waters based on 1991 and 1993 ship 

surveys. NOAA Technical Memorandum NMFS, NOAA-TM-NMFS-SWFSC-233. 

Barlow, J. and S. Sexton. 1996. The effect of diving and searching behavior on the probability of detecting trackline groups, g0, of long-diving whales during line transect surveys. Administrative Report LJ-96-14. 

Available from NMFS, Southwest Fisheries Science Center, P.O. Box 271, La Jolla, California, 92038, 

USA. 21 p. 

Barlow, J. 2003. Preliminary estimates of the abundance of cetaceans along the U.S. west coast: 1991_2001. 

Southwest Fisheries Science Center Administrative Report LJ_03_03. Available from SWFSC, 8604 La 

Jolla Shores Dr., La Jolla CA 92037. 31p. 

Berdegué, J. 2002. Depredación de las especies pelágicas reservadas a la pesca deportiva y especies en peligro de 

extinción con uso indiscriminado de artes de pesca no selectivas (palangres, FAD's, trampas para peces y 

157
redes de agallar fijas y a la deriva) por la flota palangrera Mexicana. Fundación para la conservación de los 

picudos. A.C. Mazatlán, Sinaloa, 21 de septiembre. 

Caldwell, D. K. and M. C. Caldwell. 1989. Pygmy sperm whale Kogia breviceps (de Blainville, 1838): Dwarf 

sperm whale Kogia simus Owen, 1866. pp. 235-260 In: Ridgway, S. H. and R. Harrison (eds.), Handbook 

of Marine Mammals, Vol. 4. Academic Press. 

Carretta, J.V., K.A. Forney, M.M. Muto, J. Barlow, J. Baker, and M. Lowry. 2004. U.S. Pacific Marine Mammal 

Stock Assessments: 2003. NOAA Technical Memorandum NOAA-TM-NMFS-SWFSC-358. 291p. 

Carretta, J.V. and S.J. Chivers. 2004. Preliminary estimates of marine mammal mortality and biological sampling 

of cetaceans in California gillnet fisheries for 2003. Paper SC/56/SM1 presented to the IWC Scientific 

Committee, June 2004 (unpublished). [Available from Southwest Fisheries Science Center, National 

Marine Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 92037, USA]. 

Carretta, J.V., S.J. Chivers, and K. Danil. 2005a. Preliminary estimates of marine mammal bycatch, mortality, and 

biological sampling of cetaceans in California gillnet fisheries for 2004. Administrative Report LJ-05-10, 

available from Southwest Fisheries Science Center, 8604 La Jolla Shores Drive, La Jolla, California, 

92037. 17 p. 

Carretta, J.V., T. Price, D. Petersen, and R. Read. 2005b. Estimates of marine mammal, sea turtle, and seabird 

mortality in the California drift gillnet fishery for swordfish and thresher shark, 1996-2002. Marine 

Fisheries Review 66(2):21-30. 

Forney, K.A., J. Barlow, M.M. Muto, M. Lowry, J. Baker, G. Cameron, J. Mobley, C. Stinchcomb, and J.V. 

Carretta. 2000. U.S. Pacific Marine Mammal Stock Assessments: 2000. NOAA Technical Memorandum, 

NOAA-TM-NMFS-SWFSC-300. 230p. 

Forney, K.A. 2007. Preliminary estimates of cetacean abundance along the U.S. west coast and within four 

National Marine Sanctuaries during 2005. U.S. Department of Commerce NOAA Technical 

Memorandum, NOAA-TM-NMFS-SWFSC-406. 27p. 

Holts, D. and O. Sosa-Nishizaki. 1998. Swordfish, Xiphias gladius, fisheries of the eastern North Pacific Ocean. In: 

I. Barrett, O. Sosa-Nishizaki and N. Bartoo (eds.). Biology and fisheries of swordfish, Xiphias gladius. 

Papers from the International Symposium on Pacific Swordfish, Ensenada Mexico, 11-14 December 1994. 

U.S. Dep. Commer., NOAA Tech. Rep. NMFS 142, 276 p. 

Julian, F. and M. Beeson. 1998. Estimates of mammal, turtle and bird mortality for two California gillnet fisheries: 

1990-1995. Fish. Bull. 96:271-284. 

NMFS, Southwest Region, 501 West Ocean Blvd, Long Beach, CA 90802_4213. 

Oregon Department of Fish and Game, Unpublished data. 

Richardson, W. J., C. R. Greene, Jr., C. I. Malme, and D. H. Thompson. 1995. Marine Mammals and Noise. 

Academic Press, San Diego. 576 p. 

Roest, A. I. 1970. Kogia simus and other cetaceans from San Luis Obispo County, California. J. Mammal. 51:410-

417. 

Ross, G. J. B. 1984. The smaller cetaceans of the south east coast of southern Africa. Ann. Cape Prov. Mus. Nat. 

Hist. 15:173-410. 

Sosa-Nishizaki, O., R. De la Rosa-Pacheco, R. Castro-Longoria, M. Grijalva Chon, and J. De la Rosa Velez. 1993. 

Estudio biologico pesquero del pez (Xiphias gladius) y otras especies de picudos (marlins y pez vela). Rep. 

Int. CICESE, CTECT9306. 

U.S. Department of Commerce and Secretary of the Navy. 2001. Joint Interim Report, Bahamas Marine Mammal 

Stranding Event of 15_16 March 2000. Available from NOAA, NMFS, Office of Protected Resources, 

Silver Spring, MD. 

158
Revised 10/30/2007 

DWARF SPERM WHALE (Kogia sima): 

California/Oregon/Washington Stock 

 

STOCK DEFINITION AND 

GEOGRAPHIC RANGE

 Dwarf sperm whales are 

distributed throughout deep waters 

and along the continental slopes of 

the North Pacific and other ocean 

basins (Caldwell and Caldwell 

1989; Ross 1984). This species was 

only recognized as being distinct 

from the pygmy sperm whale in 

1966 (Handley, 1966), and early 

records for the two species are 

confounded. Along the U.S. west 

coast, no at-sea sightings of this 

species have been reported; 

however, this may be partially a 

reflection of their pelagic 

distribution, small body size and 

cryptic behavior. A few sightings of 

animals identified only as Kogia sp. 

have been reported (Figure 1), and 

some of these may have been dwarf 

sperm whales. At least five dwarf 

sperm whales stranded in California 

between 1967 and 2000 (Roest 

1970; Jones 1981; J. Heyning, pers. 

comm.; NMFS, Southwest Region, 

unpublished data), and one 

stranding is reported for western 

Canada (Nagorsen and Stewart 

1983). It is unclear whether records 

of dwarf sperm whales are so rare because 

they are not regular inhabitants of this 

region, or merely because of their cryptic 

habits and offshore distribution. Available 

data are insufficient to identify any 

seasonality in the distribution of dwarf 

sperm whales, or to delineate possible stock 

boundaries. For the Marine Mammal 

Protection Act (MMPA) stock assessment 

reports, dwarf sperm whales within the Pacific U.S. Exclusive Economic Zone are divided into two 

discrete, non-contiguous areas: 1) waters off California, Oregon and Washington (this report), and 2) 

Hawaiian waters. 

OREGON

WASHINGTON

CALIFORNIA

 

POPULATION SIZE

 No information is available to estimate the population size of dwarf sperm whales off the U.S. 

west coast, as no sightings of this species have been documented despite numerous vessel surveys of this 

region (Barlow 1995; Barlow and Gerrodette 1996; Barlow 2003; Forney 2007). Based on previous 

sighting surveys and historical stranding data, it is likely that recent ship survey sightings were of pygmy 

sperm whales; K. breviceps. 

Figure 1. Kogia sightings based on aerial and 

shipboard surveys off California, Oregon and 

Washington, 1991- 2001 (see Appendix 2 for 

data sources and information on timing and 

location of survey effort). Key: ■ = Kogia 

breviceps; • = Kogia spp. Dashed line 

represents the U.S. EEZ, thin lines indicate 

completed transect effort of all surveys 

combined. 

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

45°0'0"N

40°0'0"N

159
Minimum Population Estimate

 No information is available to obtain a minimum population estimate for dwarf sperm whales. 

Current Population Trend

 Due to the rarity of records for this species along the U.S. West coast, no information exists 

regarding trends in abundance of this population. 

 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No information on current or maximum net productivity rates is available for this species. 

POTENTIAL BIOLOGICAL REMOVAL

 Based on this stock's unknown status and growth rate, the recovery factor (Fr) is 0.5, and 1⁄2Rmax is 

the default value of 0.02. However, due to the lack of abundance estimates for this species, no potential 

biological removal (PBR) can be calculated.

ANNUAL HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

 In the California drift gillnet fishery, no mortality of dwarf sperm whales or unidentified Kogia

was observed during the most recent five years of monitoring, 2000-2004 (Carretta and Chivers 2004, 

Carretta et al. 2005a, 2005b). After the 1997 implementation of a Take Reduction Plan, which included 

skipper education workshops and required the use of pingers and minimum 6-fathom extenders, overall 

cetacean entanglement rates in the drift gillnet fishery dropped considerably (Barlow and Cameron 2003). 

However, because of interannual variability in entanglement rates and the rarity of Kogia entanglements, 

additional years of data will be required to fully evaluate the effectiveness of pingers for reducing mortality 

of dwarf sperm whales. Mean annual takes in Table 1 are based on 2000-2004 data. This results in an 

average estimated annual mortality of zero dwarf sperm whales. 

 Similar drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of Baja 

California, Mexico and may take animals from this population. Quantitative data are available only for the 

Mexican swordfish drift gillnet fishery, which has increased from two vessels in 1986 to 29 vessels in 1992 

(Sosa-Nishizaki et al. 1993). The total number of sets in this fishery in 1992 can be estimated from data 

provided by these authors to be approximately 2700, with an observed rate of marine mammal bycatch of 

0.13 animals per set (10 marine mammals in 77 observed sets; Sosa-Nishizaki et al. 1993). This overall 

mortality rate is similar to that observed in California driftnet fisheries during 1990-95 (0.14 marine 

mammals per set; Julian and Beeson, 1998), but species-specific information is not available for the 

Mexican fisheries. Previous efforts to convert the Mexican swordfish driftnet fishery to a longline fishery 

have resulted in a mixed-fishery, with 20 vessels alternately using longlines or driftnets, 23 using driftnets 

only, 22 using longlines only, and seven with unknown gear type (Berdegué 2002). 

STATUS OF STOCK

 The status of dwarf sperm whales in California, Oregon and Washington waters relative to OSP is 

not known, and there are insufficient data to evaluate potential trends in abundance. No habitat issues are 

known to be of concern for this species, but in recent years questions have been raised regarding potential 

effects of human-made sounds on deep-diving cetacean species, such as dwarf sperm whales (Richardson et 

al. 1995). In particular, active sonar has been implicated in the mass stranding of beaked whales in the 

Mediterranean Sea (Frantzis 1998) and more recently in the Caribbean (U.S. Dept. of Commerce and 

Secretary of the Navy 2001). They are not listed as "threatened" or "endangered" under the Endangered 

Species Act nor as "depleted" under the MMPA. Given that this species rarely occurs off the U.S. west 

coast and current fishery mortality is zero, dwarf sperm whales off California, Oregon and Washington are 

not classified as a "strategic" stock under the MMPA. 

160
Table 1. Summary of available information on the incidental mortality and injury of dwarf sperm whales 

and unidentified Kogia sp. (California/Oregon/Washington Stock) in commercial fisheries that might take 

this species. Coefficients of variation for mortality estimates are provided in parentheses. Mean annual 

takes are based on 2000-2004 data unless noted otherwise. 

Fishery Name Data Type

Year(s) 

Percent 

Observer 

Coverage

Observed 

Mortality 

K. breviceps 

/Kogia sp.

Estimated Annual 

Mortality of K. 

breviceps/Kogia sp.

Mean 

Annual Takes 

(CV in 

parentheses)

CA/OR thresher 

shark/swordfish drift 

gillnet fishery

observer 

data

2000 

2001 

2002 

2003 

2004

22.9% 

20.4% 

22.1% 

20.2% 

20.6%

0 / 0 

0 / 0 

0 / 0 

0 / 0 

0 / 0 

0 / 0 

0 / 0 

0 / 0 

0 / 0 

0 / 0 

0

Minimum total annual takes 0

REFERENCES 

Barlow, J. 1995. The abundance of cetaceans in California waters. Part I: Ship surveys in summer and fall 

of 1991. Fish. Bull. 93:1-14. 

Barlow, J. 2003. Preliminary estimates of the abundance of cetaceans along the U.S. west coast: 1991-

2001. Southwest Fisheries Science Center Administrative Report LJ-03-03. Available from 

SWFSC, 8604 La Jolla Shores Drive, La Jolla, CA 92037. 

Barlow, J. and T. Gerrodette. 1996. Abundance of cetaceans in California waters based on 1991 and 1993 

ship surveys. NOAA Technical Memorandum NMFS, NOAA-TM-NMFS-SWFSC-233. 

Barlow, J. and S. Sexton. 1996. The effect of diving and searching behavior on the probability of 

detecting track-line groups, g0, of long-diving whales during line transect surveys. Administrative 

Report LJ-96-14. Available from NMFS, Southwest Fisheries Science Center, P.O. Box 271, La 

Jolla, California, 92038, USA. 21 p. 

Barlow, J. and G. A. Cameron. 2003. Field experiments show that acoustic pingers reduce marine mammal 

bycatch in the California drift gillnet fishery. Marine Mammal Science 19(2):265-283. 

Berdegué, J. 2002. Depredación de las especies pelágicas reservadas a la pesca deportiva y especies en 

peligro de extinción con uso indiscriminado de artes de pesca no selectivas (palangres, FAD's, 

trampas para peces y redes de agallar fijas y a la deriva) por la flota palangrera Mexicana. 

Fundación para la conservación de los picudos. A.C. Mazatlán, Sinaloa, 21 de septiembre. 

Carretta, J.V. and S.J. Chivers. 2004. Preliminary estimates of marine mammal mortality and biological 

sampling of cetaceans in California gillnet fisheries for 2003. Paper SC/56/SM1 presented to the 

IWC Scientific Committee, June 2004 (unpublished). [Available from Southwest Fisheries 

Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 

92037, USA]. 

Carretta, J.V., S.J. Chivers, and K. Danil. 2005a. Preliminary estimates of marine mammal bycatch, 

mortality, and biological sampling of cetaceans in California gillnet fisheries for 2004. 

Administrative Report LJ-05-10, available from Southwest Fisheries Science Center, 8604 La 

Jolla Shores Drive, La Jolla, California, 92037. 17 p. 

Carretta, J.V., T. Price, D. Petersen, and R. Read. 2005b. Estimates of marine mammal, sea turtle, and 

seabird mortality in the California drift gillnet fishery for swordfish and thresher shark, 1996-

2002. Marine Fisheries Review 66(2):21-30. 

Caldwell, D. K. and M. C. Caldwell. 1989. Pygmy sperm whale Kogia breviceps (de Blainville, 1838): 

Dwarf sperm whale Kogia simus Owen, 1866. pp. 235-260 In: Ridgway, S. H. and R. Harrison 

(eds.), Handbook of Marine Mammals, Vol. 4. Academic Press. 

Forney, K.A. 2007. Preliminary estimates of cetacean abundance along the U.S. west coast and within 

four National Marine Sanctuaries during 2005. U.S. Department of Commerce, NOAA Technical 

Memorandum NMFS-SWFSC-406. 27p. 

Handley, C. O. Jr. 1966. A synopsis of the genus Kogia (pygmy sperm whales). pp. 62-69 In: K. S. Norris 

(ed.), Whales, dolphins and porpoises. University of California Press, Berkeley. 

161
Jones, R. E. 1981. Food habits of smaller marine mammals from northern California. Proc. California 

Acad. Sci. 42:409-433. 

Julian, F. and M. Beeson. 1998. Estimates of mammal, turtle and bird mortality for two California gillnet 

fisheries: 1990-1995. Fish. Bull. 96:271-284. 

Nagorsen, D. W. and G. E. Stewart. 1983. A dwarf sperm whale (Kogia simus) from the Pacific coast of 

Canada. J. Mamm. 64:505-506. 

Richardson, W. J., C. R. Greene, Jr., C. I. Malme, and D. H. Thompson. 1995. Marine Mammals and 

Noise. Academic Press, San Diego. 576 p. 

Roest, A. I. 1970. Kogia simus and other cetaceans from San Luis Obispo County, California. J. 

Mammal. 51:410-417. 

Ross, G. J. B. 1984. The smaller cetaceans of the south east coast of southern Africa. Ann. Cape Prov. 

Mus. Nat. Hist. 15:173-410. 

Sosa-Nishizaki, O., R. De la Rosa-Pacheco, R. Castro-Longoria, M. Grijalva Chon, and J. De la Rosa 

Velez. 1993. Estudio biologico pesquero del pez (Xiphias gladius) y otras especies de picudos 

(marlins y pez vela). Rep. Int. CICESE, CTECT9306. 

U.S. Department of Commerce and Secretary of the Navy. 2001. Joint Interim Report, Bahamas Marine 

Mammal Stranding Event of 15_16 March 2000. Available from NOAA, NMFS, Office of 

Protected Resources, Silver Spring, MD. 

162
Revised 10/30/2007 

SPERM WHALE (Physeter macrocephalus): 

California/Oregon/Washington Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

 Sperm whales are widely 

distributed across the entire North Pacific 

and into the southern Bering Sea in 

summer but the majority are thought to be 

south of 40o

N in winter (Rice 1974; Rice 

1989; Gosho et al. 1984; Miyashita et al. 

1995). For management, the International 

Whaling Commission (IWC) had divided 

the North Pacific into two management 

regions (Donovan 1991) defined by a zigzag line which starts at 150o

W at the 

equator, is 160o

W between 40-50oN, and 

ends up at 180o

W north of 50oN; 

however, the IWC has not reviewed this 

stock boundary in many years (Donovan 

1991). Sperm whales are found yearround in California waters (Dohl et al. 

1983; Barlow 1995; Forney et al. 1995), 

but they reach peak abundance from April 

through mid-June and from the end of 

August through mid-November (Rice 

1974). They were seen in every season 

except winter (Dec.-Feb.) in Washington 

and Oregon (Green et al. 1992). Of 176 

sperm whales that were marked with 

Discovery tags off southern California in 

winter 1962-70, only three were 

recovered by whalers: one off northern 

California in June, one off Washington in 

June, and another far off British 

Columbia in April (Rice 1974). Recent 

summer/fall surveys in the eastern 

tropical Pacific (Wade and Gerrodette 

1993) show that although sperm whales 

are widely distributed in the tropics, their 

relative abundance tapers off markedly 

westward towards the middle of the 

tropical Pacific (near the IWC stock 

boundary at 150o

W) and tapers off northward towards the tip of Baja California. The structure of sperm 

whale populations in the eastern tropical Pacific is not known, but the only photographic matches of known 

individuals from this area have been between the Galapagos Islands and coastal waters of South America 

(Dufault and Whitehead 1995), suggesting that the eastern tropical animals constitute a distinct stock. A 

recent survey designed specifically to investigate stock structure and abundance of sperm whales in the 

northeastern temperate Pacific revealed no apparent hiatus in distribution between the U.S. EEZ off 

California and areas farther west, out to Hawaii (Barlow and Taylor 2005). Recent analyses of genetic 

relationships of animals in the eastern Pacific found that mtDNA and microsatellite DNA of animals 

sampled in the California Current is significantly different from animals sampled further offshore and that 

genetic differences appeared larger in an east-west direction than in a north-south direction (Mesnick et al. 

1999). 

OREGON

WASHINGTON

CALIFORNIA

Figure 1. Sperm whale sighting locations based on 

aerial and shipboard surveys off California, Oregon, 

and Washington, 1991-2005. Dashed line represents 

the U.S. EEZ, thin lines indicate completed transect 

effort of all surveys combined. See Appendix 2 for 

data sources and information on timing and location of 

survey effort. 

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

45°0'0"N

40°0'0"N

163
For the Marine Mammal Protection Act (MMPA) stock assessment reports, sperm whales within the 

Pacific U.S. EEZ are divided into three discrete, non-contiguous areas: 1) California, Oregon and 

Washington waters (this report), 2) waters around Hawaii, and 3) Alaska waters. 

POPULATION SIZE

 Barlow and Taylor (2001) estimated 1,407 (CV=0.39) sperm whales along the coasts of 

California, Oregon, and Washington during summer/fall based on ship line transect surveys within 300 nmi 

of the coast in 1993 and 1996 and 1,634 (CV=0.57) from a survey of the same area in 2001 (Barlow 2003). 

A 2005 survey of this area resulted in an abundance estimate of 3,140 (CV=0.40) whales, which is 

corrected for diving animals not seen during surveys (Forney 2007). The most recent estimate of abundance 

for this stock is the geometric mean of the 2001 and 2005 summer/autumn ship survey estimates, or 2,265 

(CV=0.34) sperm whales. A large 1982 abundance estimate for the entire eastern North Pacific (Gosho et 

al. 1984) was based on a CPUE method which is no longer accepted as valid by the International Whaling 

Commission. A combined visual and acoustic line-transect survey conducted in the eastern temperate 

North Pacific in spring 1997 resulted in estimates of 26,300 (CV=0.81) sperm whales based on visual 

sightings, and 32,100 (CV=0.36) based acoustic detections and visual group size estimates (Barlow and 

Taylor 2005). However, it is not known whether any or all of these animals routinely enter the U.S. EEZ. 

In the eastern tropical Pacific, the abundance of sperm whales has been estimated as 22,700 (95% 

C.I.=14,800-34,600; Wade and Gerrodette 1993), but this area does not include areas where sperm whales 

are taken by drift gillnet fisheries in the U.S. EEZ and there is no evidence of sperm whale movements 

from the eastern tropical Pacific to the U.S. EEZ. Barlow and Taylor (2001) also estimated 1,640 

(CV=0.33) sperm whales off the west coast of Baja California, but again there is no evidence for 

interchange between these animals and those off California, Oregon and Washington. 

 Clearly, large populations of sperm whales exist in waters that are within several thousand miles 

west and south of the California, Oregon, and Washington region that is covered by this report; however, 

there is no evidence of sperm whale movements into this region from either the west or south and genetic 

data suggest that mixing to the west is extremely unlikely. There is limited evidence of sperm whale 

movement from California to northern areas off British Columbia, but there are no abundance estimates for 

this area. The most precise and recent estimate of sperm whale abundance for this stock is therefore 2,265 

(CV=0.34) animals from the ship surveys conducted in 2001 (Barlow 2003) and 2005 (Forney 2007). This 

estimate is corrected for diving animals not seen during surveys. 

Minimum Population Estimate

 The minimum population estimate for sperm whales is taken as the lower 20th percentile of the 

log-normal distribution of abundance estimated from the 2001-2005 summer/fall ship surveys off 

California, Oregon and Washington (Barlow 2003; Forney 2007) or approximately 1,719. 

Current Population Trend

 Sperm whale abundance appears to have been rather variable off California between 1979/80 and 

1996 (Barlow 1994; Barlow 1997) but does not show any obvious trends. Although the population in the 

eastern North Pacific is expected to have grown since large-scale pelagic whaling stopped in 1980, the 

possible effects of large unreported catches are unknown (Yablokov 1994) and the ongoing incidental ship 

strikes and gillnet mortality make this uncertain. 

 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 There are no published estimates of the growth rate for any sperm whale population (Best 1993). 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for the California portion of this stock is calculated 

as the minimum population size (1,719) times one half the default maximum net growth rate for cetaceans 

(1⁄2 of 4%) times a recovery factor of 0.1 (the default value for an endangered species), resulting in a PBR 

of 3.4. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Historic Whaling

164
 Between 1800 and 1909, about 60,842 sperm whales were estimated taken in the North Pacific 

(Best 1976). The reported take of North Pacific sperm whales by commercial whalers between 1947 and 

1987 totaled 258,000 (C. Allison, pers. comm.). Ohsumi (1980) lists an additional 28,198 sperm whales 

taken mainly in coastal whaling operations from 1910 to 1946. Based on the massive under-reporting of 

Soviet catches, Brownell et al. (1998) estimate that about 89,000 whales were additionally taken by the 

Soviet pelagic whaling fleet between 1949 and 1979. The Japanese coastal operations apparently also 

under-reported catches by an unknown amount (Kasuya 1998). Thus a total of at least 436,000 sperm 

whales were taken between 1800 and the end of commercial whaling for this species in 1987. Of this grand 

total, an estimated 33,842 were taken by Soviet and Japanese pelagic whaling operations in the eastern 

North Pacific from the longitude of Hawaii to the U.S. West coast, between 1961 and 1976 (Allen 1980, 

IWC statistical Areas II and III), and 965 were reported taken in land-based U.S. West coast whaling 

operations between 1947 and 1971 (Ohsumi 1980). In addition, 13 sperm whales were taken by shore 

whaling stations in California between 1919 and 1926 (Clapham et al. 1997). There has been a prohibition 

on taking sperm whales in the North Pacific since 1988, but large-scale pelagic whaling stopped earlier, in 

1980. 

Fishery Information 

 The offshore drift gillnet fishery is the only fishery that is likely to take sperm whales from this 

stock. Detailed information on this fishery is provided in Appendix 1. A summary of known fishery 

mortality and injury for this stock of sperm whales from 2000-2004 is given in Table 1. After the 1997 

implementation of a Take Reduction Plan, which included skipper education workshops and required the 

use of pingers and minimum 6-fathom extenders, overall cetacean entanglement rates in the drift gillnet 

fishery dropped considerably (Barlow and Cameron 2003). However, two sperm whales have been 

observed taken in nets with pingers (1996 and 1998). Because sperm whale entanglement is rare and 

because those nets which took sperm whales did not use the full mandated complement of pingers, it is 

difficult to evaluate whether pingers have any effect on sperm whale entanglement in drift gillnets. One 

sperm whale stranded dead in 2004 with 5 to 6-inch mesh nylon netting found in its stomach (NMFS 

Southwest Regional Office, unpublished data). The fishery source of this netting is unknown. Mean 

annual takes for this fishery (Table 1) are based on 2000-2004 data. This results in an average estimate of 

0.2 (CV = not available) sperm whale mortalities per year. 

Table 1. Summary of available information on the incidental mortality and injury of sperm whales 

(CA/OR/WA stock) for commercial fisheries that might take this species (Carretta and Chivers 2004, 

Carretta et al. 2005a, 2005b). n/a indicates that data are not available. Mean annual takes are based on 

2000-2004 data unless noted otherwise. 

Fishery Name Year(s) Data 

Type 

Percent 

Observer 

Coverage 

Observed 

mortality (and 

injury in 

parentheses) 

Estimated 

mortality (CV 

in 

parentheses) 

Mean annual 

takes (CV in 

parentheses) 

CA/OR thresher 

shark/swordfish 

drift gillnet fishery 

2000 

2001 

2002 

2003 

2004 

Observer 

data 

22.9% 

20.4% 

22.1% 

20.2% 

20.6% 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0 (n/a) 

Unknown fishery 2000-2004 stranding n/a 1 ≥1 ≥0.2 

Total annual takes ≥0.2 (n/a) 

 Drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of Baja 

California, Mexico and may take animals from this population. Quantitative data are available only for the 

Mexican swordfish drift gillnet fishery, which uses vessels, gear, and operational procedures similar to 

those in the U.S. drift gillnet fishery, although nets may be up to 4.5 km long (Holts and Sosa-Nishizaki 

1998). The fleet increased from two vessels in 1986 to 31 vessels in 1993 (Holts and Sosa-Nishizaki 1998). 

The total number of sets in this fishery in 1992 can be estimated from data provided by these authors to be 

approximately 2700, with an observed rate of marine mammal bycatch of 0.13 animals per set (10 marine 

mammals in 77 observed sets; Sosa-Nishizaki et al. 1993). This overall mortality rate is similar to that 

observed in California driftnet fisheries during 1990-95 (0.14 marine mammals per set; Julian and Beeson, 

165
1998), but species-specific information is not available for the Mexican fisheries. Previous efforts to 

convert the Mexican swordfish driftnet fishery to a longline fishery have resulted in a mixed-fishery, with 

20 vessels alternately using longlines or driftnets, 23 using driftnets only, 22 using longlines only, and 

seven with unknown gear type (Berdegué 2002). 

Ship Strikes

 No sperm whale mortalities have been attributed to ship strikes during the period 2000-2004. 

STATUS OF STOCK

 The only estimate of the status of North Pacific sperm whales in relation to carrying capacity 

(Gosho et al. 1984) is based on a CPUE method which is no longer accepted as valid. Sperm whales are 

formally listed as "endangered" under the Endangered Species Act (ESA), and consequently the California 

to Washington stock is automatically considered as a "depleted" and "strategic" stock under the MMPA. 

The annual rate of kill and serious injury ( 0.2 per year) is less than the calculated PBR for this stock ( 3.4). 

Total fishery takes may not be approaching zero mortality and serious injury rate. Increasing levels of 

anthropogenic sound in the world’s oceans has been suggested to be a habitat concern for whales, 

particularly for deep-diving whales like sperm whales that feed in the ocean’s “sound channel”. 

REFERENCES

Allison, C. International Whaling Commission. The Red House, 135 Station Road, Impington, Cambridge, 

UK CB4 9NP. 

Allen, K. R. 1980. Size distribution of male sperm whales in the pelagic catches. Rep. Int. Whal. Commn. 

Special Issue 2:51-56. 

Barlow, J. 1994. Abundance of large whales in California coastal waters: a comparison of ship surveys in 

1979/80 and in 1991. Rept. Int. Whal. Commn. 44:399-406. 

Barlow, J. 1995. The abundance of cetaceans in California waters. Part I: Ship surveys in summer and fall 

of 1991. Fish. Bull. 93:1-14. 

Barlow, J. 1997. Preliminary estimates of cetacean abundance off California, Oregon and Washington 

based on a 1996 ship survey and comparisons of passing and closing modes. Administrative 

Report LJ-97-11, Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. 

Box 271, La Jolla, CA 92038. 25p. 

Barlow, J., R. W. Baird, J. E. Heyning, K. Wynne, A. M. Manville, II, L. F. Lowry, D. Hanan, J. Sease, and 

V. N. Burkanov. 1994. A review of cetacean and pinniped mortality in coastal fisheries along the 

west coast of the U.S. and Canada and the east coast of the Russian Federation. Rep. Int. Whal. 

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168
Revised 10/30/2007 

HUMPBACK WHALE (Megaptera novaeangliae): 

 California/Oregon/Washington Stock

 STOCK DEFINITION AND GEOGRAPHIC 

RANGE

 Although the International Whaling 

Commission (IWC) only considered one stock 

(Donovan 1991), there is now good evidence for 

multiple populations of humpback whales in the 

North Pacific (Johnson and Wolman 1984; Baker 

et al. 1990). Humpback whales in the North 

Pacific feed in coastal waters from California to 

Russia and in the Bering Sea. They migrate south 

to wintering destinations off Mexico, Central 

America, Hawaii, southern Japan, and the 

Philippines. Mitochondrial and nuclear genetic 

markers show that considerable structure exists in 

humpback whale populations in the North Pacific 

(Baker et al. 1998). Significant levels of 

mitochondrial and nuclear genetic differences were 

found between central California and Southeast 

Alaska feeding areas (Baker et al. 1998). 

Mitochondrial genetic differences are also found 

between feeding area in the Atlantic (Palsboll et al. 

1995). The genetic exchange rate between 

California and Alaska is estimated to be less than 1 

female per generation (Baker 1992). Two breeding 

areas (Hawaii and coastal Mexico) showed fewer 

genetic differences than did the two feeding areas 

(Baker 1992). Individually identified whales have 

been found to move between winter breeding areas 

in Hawaii and Mexico (Baker et al. 1990). There 

have been no individual matches between 597 

humpbacks photographed in California and 617 

humpbacks photographed in Alaska (Calambokidis 

et al. 1996). Only two of the 81 whales 

photographed in British Columbia have matched with 

a California catalog (Calambokidis et al. 1996), 

indicating that the U.S./Canada border is an 

approximate geographic boundary between feeding 

populations. Waters off northern Washington may be 

an area of mixing between the 

California/Oregon/Washington stock and a southern British Columbia stock. For humpback whales, maternally 

directed fidelity to specific feeding areas within an ocean basin appears to be so strong that genetic differences have 

evolved in both the Atlantic, where there is a single breeding area, and in the Pacific, where there are multiple 

breeding areas. Because fidelity appears to be greater in feeding areas than in breeding areas, the stock structure of 

humpback whales is defined based on feeding areas. 

OREGON

WASHINGTON

CALIFORNIA

For the Marine Mammal Protection Act (MMPA) stock assessment reports, the 

California/Oregon/Washington Stock is defined to include humpback whales that feed off the west coast of the 

United States. The winter migratory destination of this stock is primarily in coastal waters of Mexico and Central 

America. Two other stocks are recognized in the U.S. MMPA stock assessment reports: the Central North Pacific 

Stock (with feeding areas from Southeast Alaska to the Alaska Peninsula) and the Western North Pacific Stock (with 

feeding areas from the Aleutian Islands, the Bering Sea, and Russia). 

Figure 1. Humpback whale sightings based on 

shipboard surveys off California, Oregon, and 

Washington, 1991- 2005. Dashed line represents 

the U.S. EEZ, thin lines indicate completed 

transect effort of all surveys combined. See 

Appendix 2 for data sources and information on 

timing and location of survey effort. 

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

45°0'0"N

40°0'0"N

169
POPULATION SIZE

 Based on whaling statistics, the pre-1905 population of humpback whales in the North Pacific was 

estimated to be 15,000 (Rice 1978), but this population was reduced by whaling to approximately 1,200 by 1966 

(Johnson and Wolman 1984). The North Pacific total now almost certainly exceeds 6,000 humpback whales 

(Calambokidis et al. 1997). Estimates of the abundance of the eastern Pacific stock of humpback whales were made 

by aerial survey (Dohl 1983; Forney et al. 1995) and ship surveys (Barlow 1995), but those estimates are now over 9 

years old and the aerial estimates did not include correction factors for diving whales that would be missed. More 

recent estimates are available from ship surveys and mark-recapture studies. Barlow (2003) estimated 1,109 

(CV=0.36) humpbacks in California, Oregon, and Washington waters based on summer/fall ship line-transect 

surveys in 2001. Forney (2007) estimated 1,769 (CV=0.16) humpbacks in the same region based on a 2005 

summer/fall ship line-transect survey. Calambokidis et al. (2004) estimated humpback whale abundance in these 

feeding areas from 1991 to 2003 using Petersen mark-recapture estimates based on photo-identification collections 

in adjacent pairs of years (Figure 2). These data show a general upward trend in abundance followed by a large (but 

not statistically significant) drop in the 1999/2000 and 2000/2001 estimates. The 2002/2003 mark-recapture 

population estimate (1,391, CV=0.22) is higher than any previous estimates and may indicate that the apparent 

decline in the previous two estimates exaggerates any real decline that might have occurred (Calambokidis et al. 

2003) or that a real decline was followed by an influx of new whales from another area (Calambokidis et al. 2004). 

This latter view is substantiated by the greater fraction of new whales seen for the first time in 2003 (Calambokidis 

et al. 2004). In general, mark-recapture estimates are negatively biased due to heterogeneity in sighting probabilities 

(Hammond 1986); however, this bias is likely to be minimal because the above mark-recapture estimate is based 

on data from nearly half of the entire population (the 2002/2003 data contained 542 known individuals). The 

combined 2001-2005 line transect estimate of 1,401 (CV=0.19) is more precise than recent mark-recapture estimates 

and represents the most recent abundance information for this stock of humpback whales. The best estimate of 

abundance is the unweighted geometric mean of 2002/2003 mark-recapture and 2001-2005 line transect estimates, 

or 1,396 (CV=0.15) whales. 

 

Minimum Population Estimate

 The minimum population 

estimate for humpback whales in the 

California/Mexico stock is taken as the 

lower 20th percentile of the log-normal 

distribution of the unweighted mean 

estimate or approximately 1,236. 

Current Population Trend

Ship surveys provide some 

indication that humpback whales 

increased in abundance in California 

coastal waters between 1979/80 and 

1991 (Barlow 1994) and between 1991 

and 2005 (Barlow 2003; Forney 2007), 

but this increase was not steady, and 

estimates showed a slight dip in 2001. 

Mark-recapture population estimates 

increased steadily from 1988/90 to 

1997-98 at about 8% per year 

(Calambokidis et al. 1999), showed a 

decrease around 1999-2001, and then 

increased again in 2002-2003 (Figure 2, 

Calambokidis et al. 2004) The observed decrease in abundance between 1999-2001 may have been related to 

prevailing oceanographic conditions off the U.S. west coast. The apparent dip in the 1999/2000 and 2000/2001 

estimates may indicate that population growth is slowing, but the subsequent increases in 2001/2002 and 2002/2003 

casts some doubt on this explanation. Population estimates for the entire North Pacific have also increased 

substantially from 1,200 in 1966 to 6,000-8,000 circa 1992. Although these estimates are based on different 

methods and the earlier estimate is extremely uncertain, the growth rate implied by these estimates (6-7%) is 

consistent with the recently observed growth rate of the eastern North Pacific stock. 

0

500

1000

1500

2000

1990 1992 1994 1996 1998 2000 2002

Figure 2. Mark-recapture estimates of the abundance of humpback

whales feeding off California, Oregon, and Washington, based on 

photo-identification studies (Calambokidis et al. 2004). Dotted lines 

indicate +/- 2 standard errors for each estimate. Straight, bold line 

indicates linear regression. 

170
CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 The proportion of calves in the California/Mexico stock from 1986 to 1994 appeared much lower than 

previously measured for humpback whales in other areas (Calambokidis and Steiger 1994), but in 1995-97 a greater 

proportion of calves were identified, and the 1997 reproductive rates for this population are closer to those reported 

for humpback whale populations in other regions (Calambokidis et al. 1998). Despite the apparently low proportion 

of calves, two independent lines of evidence indicate that this stock was growing in the 1980s and early 1990s 

(Barlow 1994; Calambokidis et al. 2003) with a best estimate of 8% growth per year (Calambokidis et al. 1999). 

The current net productivity rate is unknown. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size ( 

1,236) times one half the estimated population growth rate for this stock of humpback whales (1⁄2 of 8%) times a 

recovery factor of 0.1 (for an endangered species with Nmin < 1,500), resulting in a PBR of 4.9. Because this stock 

spends approximately half its time outside the U.S. EEZ, the PBR allocation for U.S. waters is 2.5 whales per year.

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Historic Whaling 

 The reported take of North Pacific humpback whales by commercial whalers totaled approximately 7,700 

between 1947 and 1987 (C. Allison, IWC unpubl. data). In addition, approximately 7,300 were taken along the west 

coast of North America from 1919 to 1929 (Tonnessen and Johnsen 1982). Total 1910-1965 catches from the 

California-Washington stock includes at least the 2,000 taken in Oregon and Washington, the 3,400 taken in 

California, and the 2,800 taken in Baja California (Rice 1978). Shore-based whaling apparently depleted the 

humpback whale stock off California twice: once prior to 1925 (Clapham et al. 1997) and again between 1956 and 

1965 (Rice 1974). There has been a prohibition on taking humpback whales since 1966. 

Fishery Information

 A summary of known fishery mortality and injury for this stock of humpback whales for 2000-2004 is 

given in Table 1. Detailed information on these fisheries is provided in Appendix 1. After the 1997 implementation 

of a Take Reduction Plan, which included skipper education workshops and required the use of pingers and 

minimum 6-fathom extenders, overall cetacean entanglement rates in the drift gillnet fishery dropped considerably 

(Barlow and Cameron 2003). Mean annual takes for this fishery (Table 1) are based on 2000-2004 data. This 

results in an average estimate of zero humpback whales taken annually. Some gillnet mortality of large whales may 

go unobserved because whales swim away with a portion of the net. The deaths of two humpback whales that 

stranded in the Southern California Bight have been attributed to entanglement in fishing gear (Heyning and Lewis 

1990), and a humpback whale was observed off Ventura, CA in 1993 with a 20 ft section of netting wrapped around 

and trailing behind. Other unobserved fisheries may also result in injuries or deaths of humpback whales. During 

the period 2000-2004, there were nine humpbacks observed entangled with line, buoys, and/or trap pot gear. Some 

of these animals were females with calves. The final status of all these whales is unknown. 

 Drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of Baja California, 

Mexico and may take animals from the same population. Quantitative data are available only for the Mexican 

swordfish drift gillnet fishery, which uses vessels, gear, and operational procedures similar to those in the U.S. drift 

gillnet fishery, although nets may be up to 4.5 km long (Holts and Sosa-Nishizaki 1998). The fleet increased from 

two vessels in 1986 to 31 vessels in 1993 (Holts and Sosa-Nishizaki 1998). The total number of sets in this fishery 

in 1992 can be estimated from data provided by these authors to be approximately 2700, with an observed rate of 

marine mammal bycatch of 0.13 animals per set (10 marine mammals in 77 observed sets; Sosa-Nishizaki et al. 

1993). This overall mortality rate is similar to that observed in California driftnet fisheries during 1990-95 (0.14 

marine mammals per set; Julian and Beeson, 1998), but species-specific information is not available for the Mexican 

fisheries. Previous efforts to convert the Mexican swordfish driftnet fishery to a longline fishery have resulted in a 

mixed-fishery, with 20 vessels alternately using longlines or driftnets, 23 using driftnets only, 22 using longlines 

only, and seven with unknown gear type (Berdegué 2002). 

 

171
Table 1. Summary of available information on the incidental mortality and injury of humpback whales (eastern 

North Pacific stock) for commercial fisheries that might take this species ( Carretta and Chivers 2004, Carretta et al. 

2005a, 2005b). Injury includes any entanglement that does not result in immediate death and may include serious 

injury resulting in death. n/a indicates that data are not available. Mean annual takes are based on 2000-2004 data 

unless noted otherwise. 

Fishery Name Year(s) Data Type 

Percent 

Observer 

Coverage 

Observed 

Mortality (and 

injury) 

Estimated mortality 

Mean Annual 

Takes 

CA/OR thresher 

shark/swordfish drift 

gillnet fishery 

2000 

2001 

2002 

2003 

2004 

Observer 

data 

22.9% 

20.4% 

20.0% 

20.3% 

20.6% 

0 

0 

0 

0 

0 

Mortality 

0,0,0,0,0 

Injury 

0,0,0,0,0 

Mortality 

0 

Injury 

0 

CA angel shark/halibut 

and other species large 

mesh (>3.5”) set gillnet 

fishery 

1990-94 

2001 

2002 

2003 

2004 

2005 

No fisherywide 

observer 

program 

since 1994 

10-15% 

0% 

0% 

0% 

0% 

0% 

0,0,0,0,0 

 n/a n/a n/an/a 

n/a 

0,0,0,0,0 

 n/a n/a n/an/an/a 

 n/a 

Unidentified fisheries 2000-2004 Strandings& 

sightings n/a 

0 

 (9) 

n/a > 1.8 

 Total Annual Takes > 1.8 

Ship Strikes 

Ship strikes were implicated in the deaths of at least two humpback whales in 1993, one in 1995, and one in 

2000 (NMFS, Southwest Regional Office, unpubl. data). During 2000-2004, there were an additional five injuries 

and three mortalities of unidentified large whales attributed to ship strikes. Additional mortality from ship strikes 

probably goes unreported because the whales do not strand or, if they do, they do not have obvious signs of trauma. 

Several humpback whales have been photographed in California with large gashes in their dorsal surface that appear 

to be from ship strikes (J. Calambokidis, pers. comm.). The average number of humpback whale deaths by ship 

strikes for 2000-2004 is at least 0.2 per year. 

Other human-caused mortality

 A humpback whale died and stranded near Moss Landing in 2000 with synthetic (possibly nylon) line 

wrapped around its flukes. The origin of this line (fishery or other anthropogenic source) is unknown. The average 

number of humpback deaths from unknown anthropogenic sources is 0.2 per year from 2000-2004. 

STATUS OF STOCK

 As a result of commercial whaling, humpback whales were formally listed as "endangered" under the 

Endangered Species Act (ESA) in 1973. The species is still listed as “endangered”, and consequently the 

California/Mexico stock is automatically considered as a "depleted" and "strategic" stock under the MMPA. The 

estimated annual mortality and injury due to entanglement (1.8/yr), other anthropogenic sources (0.2/yr), plus ship 

strikes (0.2/yr) in California is less than the PBR allocation of 2.5 for U.S. waters. The nine humpbacks that were 

entangled at sea may have been seriously injured. Based on strandings and at sea observations, annual humpback 

whale mortality and serious injury in commercial fisheries may be greater than 10% of the PBR; therefore, total 

fishery mortality may not be approaching zero mortality and serious injury rate. The eastern North Pacific stock 

appears to be increasing in abundance. 

Habitat Concerns 

Increasing levels of anthropogenic sound in the world’s oceans (Andrew et al. 2002), such as those 

produced by shipping traffic, ATOC (Acoustic Thermometry of Ocean Climate) or LFA (Low Frequency Active) 

sonar, have been suggested to be a habitat concern for whales, particularly for baleen whales that may communicate 

using low-frequency sound. 

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Straley, C. S. Baker, O. von Ziegesar, M. E. Dahlheim, J. M. Waite, J. D. Darling, G. Ellis, and G. A. 

Green. 1996. Interchange and isolation of humpback whales in California and other North Pacific feeding 

grounds. Mar. Mamm. Sci. 12(2):215-226. 

Calambokidis, J., G. H. Steiger, J. M. Straley, T. J. Quinn, II, L. M. Herman, S. Cerchio, D. R. Salden, M. 

Yamaguchi, F. Sato, J. Urbán R., J. Jacobsen, O. von Ziegesar, K. C. Balcomb, C. M. Gabriele, M. E. 

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O. von Ziegesar, K. C. Balcomb, C. M. Gabriele, M. E. Dahlheim, S. Uchida, G. Ellis, Y. Miyamura, P. 

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Mamm. Sci. 17(4):769-794. 

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Pacific coast of Mexico. 

175
Revised 10/30/2007

BLUE WHALE (Balaenoptera musculus): Eastern North Pacific Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

 The International Whaling Commission 

(IWC) has formally considered only one 

management stock for blue whales in the North 

Pacific (Donovan 1991), but this ocean is thought 

to include more than one population (Ohsumi and 

Wada 1972; Braham 1991), possibly as many as 

five (Reeves et al. 1998). Blue whales in the 

North Pacific produce two distinct, stereotypic 

calls that have been termed the northwestern and 

northeastern call types, and it has been proposed 

that these represent two distinct populations with 

some degree of geographic overlap (Stafford et al. 

2001). The northeastern call predominates in the 

Gulf of Alaska, the U.S. West Coast, and the 

eastern tropical Pacific, and the northwestern call 

predominates from south of the Aleutian Islands to 

the Kamchatka Peninsula in Russia (Stafford et al. 

2001). Both call types are represented in lower 

latitudes in the central North Pacific but differ in 

their seasonal patterns (Stafford et al. 2001). 

Gilpatrick and Perryman (submitted) showed that 

blue whales from California to Central America are 

on average about two meters shorter than blue 

whales from the central and western north Pacific 

regions. Mate et al. (1999) used satellite tags to 

show that the eastern tropical Pacific is a migratory 

destination for blue whales that were tagged off 

southern California, and photographs of blue 

whales on the Costa Rica Dome in the eastern 

tropical Pacific have matched individuals that had 

been previously photographed off California 

(Calambokidis, pers. comm.). Photographs of blue 

whales in California have also been matched to 

individuals photographed off the Queen Charlotte 

Islands in northern British Columbia 

(Calambokidis, pers. comm.) and to one individual 

photographed in the northern Gulf of Alaska 

(Calambokidis and Barlow, pers. comm.). 

For the Marine Mammal Protection Act 

(MMPA) stock assessment reports, the Eastern North Pacific Stock of blue whales includes animals found in the 

eastern North Pacific from the northern Gulf of Alaska to the eastern tropical Pacific. This definition is consistent 

with both the distribution of the northeastern call type and with the known range of photographically identified 

individuals. Based on locations where the northeastern call type has been recorded, some individuals in this stock 

may range as far west as Wake Island and as far south as the Equator (Stafford et al. 1999, 2001). The U.S. West 

Coast is certainly one of the most important feeding areas in summer and fall (Figure 1), but, increasingly, blue 

whales from this stock have been found feeding to the north and south of this area during summer and fall. Most of 

this stock is believed to migrate south to spend the winter and spring in high productivity areas off Baja California, 

in the Gulf of California, and on the Costa Rica Dome. Given that these migratory destinations are areas of high 

productivity and given the observations of feeding in these areas, blue whales can be assumed to feed year round. 

Some individuals from this stock may be present year-round on the Costa Rica Dome (Reilly and Thayer 1990). 

OREGON

WASHINGTON

CALIFORNIA

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

40°0'0"N

45°0'0"N

Figure 1. Blue whale sighting locations based on aerial 

and summer/autumn shipboard surveys off California, 

Oregon, and Washington, 1991-2005 (see Appendix 2 for 

data sources and information on timing and location of 

surveys). Dashed line represents the U.S. EEZ; thin lines 

represent completed transect effort for all surveys 

combined.

176
However, it is also possible that some Southern Hemisphere blue whales might occur north of the equator during the 

austral winter. One other stock of North Pacific blue whales (in Hawaiian waters) is recognized in the Marine 

Mammal Protection Act (MMPA) Stock Assessment Reports. 

POPULATION SIZE 

 The size of the feeding stock of blue whales off the U.S. West Coast was estimated recently by both linetransect and mark-recapture methods. Barlow (2003) estimated 888 (CV=0.40) blue whales off California, Oregon, 

and Washington based on ship line-transect surveys in 2001 and Forney (2007), estimated 721 (CV=0.27) from a 

2005 line-transect survey of the same area. The unweighted geometric mean of the 2001 and 2005 line transect 

estimates is 800 (CV=0.24) whales. Calambokidis et al. (2003) used photographic mark-recapture and estimated 

population sizes of 1,567 (CV=0.32) based on 2000-2002 photographs of left sides and 1,953 (CV=0.33) based on 

right sides. The average of the mark-recapture estimates is 1,760 (CV=0.32) whales. . Mark-recapture estimates are 

often negatively biased by individual heterogeneity in sighting probabilities (Hammond 1986); however, 

Calambokidis et al. 2003 minimize such effects by selecting one sample that was taken randomly with respect to 

distance from the coast. Similarly, the line-transect estimates may also be negatively biased because some blue 

whales in this stock are outside of the study area at the time of survey (Calambokidis and Barlow 2004). The best 

estimate of blue whale abundance is the unweighted geometric mean of the line-transect and mark-recapture 

estimates, or 1,186 (CV=0.19). 

Minimum Population Estimate 

 The minimum population estimate for blue whales is taken as the lower 20th percentile of the log-normal 

distribution of abundance estimated from the combined mark-recapture and line-transect estimates, or approximately 

1,005. 

Current Population Trend 

There is some indication that blue whales increased in abundance in California coastal waters between 

1979/80 and 1991 (regression p<0.05, Barlow 1994) and between 1991 and 1996 (not significant, Barlow 1997). 

Although this may be due to an increase in the stock as a whole, it could also be the result of an increased use of 

California as a feeding area. The size of the apparent increase in abundance seen by Barlow (1994) is too large to be 

accounted for by population growth alone. Also, Larkman and Veit (1998) did not detect any increase along 

consistently surveyed tracklines in the Southern California Bight from 1987 to 1995. Although the population in the 

North Pacific is expected to have grown since being given IWC protected status in 1966, there is no evidence 

showing that the eastern North Pacific stock is currently growing. Estimates from line transect surveys declined 

between 1991-2005 (Figure 2), which is probably due to interannual variability in the fraction of the population that 

utilizes California waters during the summer and autumn. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No information exists on the rate of growth of blue whale populations in the Pacific (Best 1993). 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size 

(1,005) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.1 

(for an endangered species which has a minimum abundance less than 1,500), resulting in a PBR of 2.0. Because 

this stock spends approximately half its time outside the U.S. EEZ, the PBR allocation for U.S. waters is half this 

total, or 1.0 whales per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Historic Whaling 

 The reported take of North Pacific blue whales by commercial whalers totaled 9,500 between 1910 and 

1965 (Ohsumi and Wada 1972). Approximately 2,000 were taken off the west coast of North America between 

1919 and 1929 (Tonnessen and Johnsen 1982). Partially overlapping with this is Rice's (1992) report of at least 

1,378 taken by factory ships off California and Baja California between 1913 and 1937. Shore-based whaling 

stations in central California took 3 blue whales between 1919 and 1926 (Clapham et al. 1997) and 48 blue whales 

between 1958 and 1965 (Rice 1974). Additional blue whales were killed during this period from land-stations in 

British Columbia. Blue whales in the North Pacific were given protected status by the IWC in 1966, but 

177
Doroshenko (2000) reported that a small number of blue whales were taken illegally by Soviet whalers after that 

date. 

Figure 2. Estimates of abundance from vessel-based line transect (LT) and mark-recapture (MR) surveys conducted 

in California waters, 1991-2005 (Barlow 2003; Calambokidis et al. 2003; Calambokidis and Barlow 2004; Forney 

2007). The four line transect estimates are based on one 1991-93 pooled estimate and three annual surveys 

conducted in 1996, 2001, and 2005, respectively. The three mark-recapture estimates are based on 1991-93, 1995-

97, and 2000-02 pooled estimates, respectively.

Fisheries Information 

 The offshore drift gillnet fishery is the only fishery that is likely to take blue whales from this stock, but no 

fishery mortalities or serious injuries have been observed (Table 1). Detailed information on this fishery is provided 

in Appendix 1. After the 1997 implementation of a Take Reduction Plan, which included skipper education 

workshops and required the use of pingers and minimum 6-fathom extenders, overall cetacean entanglement rates in 

the drift gillnet fishery dropped considerably (Barlow and Cameron 1999). Mean annual takes for this fishery 

(Table 1) are based only on 2000-2004 data. This results in an average estimate of zero blue whales taken annually. 

Some gillnet mortality of large whales may go unobserved because whales swim away with a portion of the net; 

however, fishermen report that large rorquals (blue and fin whales) usually swim through nets without entangling 

and with very little damage to the nets. 

 Drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of Baja California, 

Mexico and may take animals from the same population. Quantitative data are available only for the Mexican 

swordfish drift gillnet fishery, which uses vessels, gear, and operational procedures similar to those in the U.S. drift 

gillnet fishery, although nets may be up to 4.5 km long (Holts and Sosa-Nishizaki 1998). The fleet increased from 

two vessels in 1986 to 31 vessels in 1993 (Holts and Sosa-Nishizaki 1998). The total number of sets in this fishery 

in 1992 can be estimated from data provided by these authors to be approximately 2700, with an observed rate of 

178
marine mammal bycatch of 0.13 animals per set (10 marine mammals in 77 observed sets; Sosa-Nishizaki et al. 

1993). This overall mortality rate is similar to that observed in California driftnet fisheries during 1990-95 (0.14 

marine mammals per set; Julian and Beeson, 1998), but species-specific information is not available for the Mexican 

fisheries. Previous efforts to convert the Mexican swordfish driftnet fishery to a longline fishery have resulted in a 

mixed-fishery, with 20 vessels alternately using longlines or driftnets, 23 using driftnets only, 22 using longlines 

only, and seven with unknown gear type (Berdegué 2002). 

Table 1. Summary of available information on the incidental mortality and injury of blue whales (Eastern North 

Pacific stock) for commercial fisheries that might take this species (Carretta and Chivers 2004, Carretta et al. 2005a, 

2005b). Mean annual takes are based on 2000-2004 data unless noted otherwise. 

Fishery Name Year(s) Data Type 

Percent 

Observer 

Coverage 

Observed 

Mortality (and 

injury) 

Estimated 

mortality 

(CV in 

parentheses) 

Mean 

Annual 

Takes 

(CV in 

parentheses) 

CA/OR thresher 

shark/swordfish drift gillnet 

fishery 

2000 

2001 

2002 

2003 

2004 

Observer 

data 

22.9% 

20.4% 

20.0% 

20.2% 

20.6% 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0 

 Total Annual Takes 0 

Ship Strikes 

Ship strikes were implicated in the deaths of blue whales in 1980, 1986, 1987, 1993, 2002 and 2004 (J. 

Cordaro, Southwest Region, NMFS and J. Heyning, pers. comm.). In addition, there was one blue whale injured as 

the result of a ship strike in 2003 (blood observed in the water). During 2000-2004, there were an additional five 

injuries and three mortalities of unidentified large whales attributed to ship strikes. Additional mortality from ship 

strikes probably goes unreported because the whales do not strand or, if they do, they do not always have obvious 

signs of trauma. Several blue whales have been photographed in California with large gashes in their dorsal surface 

that appear to be from ship strikes (J. Calambokidis, pers. comm.). The average number of blue whale mortalities 

and injuries in California attributed to ship strikes was 0.6 per year for 2000-2004. 

STATUS OF STOCK

 As a result of commercial whaling, blue whales were formally listed as "endangered" under the Endangered 

Species Act (ESA) in 1973. They are still listed as “endangered”, and consequently the Eastern North Pacific stock 

is automatically considered as a "depleted" and "strategic" stock under the MMPA. The annual incidental mortality 

and injury rate (0.6/year) from ship strikes is less than the calculated PBR (1.0) for this stock, but this rate does not 

include unidentified large whales struck by vessels, some of which may have been blue whales. To date, no blue 

whale mortality has been associated with California gillnet fisheries; therefore, total fishery mortality is approaching 

zero mortality and serious injury rate. 

Habitat Concerns 

Increasing levels of anthropogenic sound in the world’s oceans (Andrew et al. 2002) have been suggested 

to be a habitat concern for blue whales (Reeves et al. 1998). 

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1257. 

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46:15-19. 

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Meeting of the International Whaling Commission. 20 pp. 

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Pacific. Mar. Mamm. Sci. 6(4):265-277. 

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(Balaenoptera musculus). Office of Protected Resources, NMFS, NOAA, Silver Spring, Maryland. 30 pp. 

Sosa-Nishizaki, O., R. De la Rosa Pacheco, R. Castro Longoria, M. Grijalva Chon, and J. De la Rosa Velez. 1993. 

Estudio biologico pesquero del pez (Xiphias gladius) y otras especies de picudos (marlins y pez vela). Rep. 

Int. CICESE, CTECT9306. 

Stafford, K. M., S. L. Nieukirk, and C. G. Fox. 1999. An acoustic link between blue whales in the eastern tropical 

Pacific and the Northeast Pacific. Mar. Mamm. Sci. 15(4):1258-1268. 

Stafford, K. M., S. L. Nieukirk, and C. G. Fox. 2001. Geographic and seasonal variation of blue whale calls in the 

North Pacific. Journal Cetacean Research and Management. 3:65-76. 

Tonnessen, J. N., and A. O. Johnsen. 1982. The History of Modern Whaling. Univ. Calif. Press, Berkeley and Los 

Angeles. 798 pp. 

Wade, P. R. and T. Gerrodette. 1993. Estimates of cetacean abundance and distribution in the eastern tropical 

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Yablokov, A. V. 1994. Validity of whaling data. Nature 367:108. 

181
Revised 10/30/2007 

FIN WHALE (Balaenoptera physalus): 

California/Oregon/Washington Stock 

STOCK DEFINITION AND 

GEOGRAPHIC RANGE

 The International Whaling 

Commission (IWC) recognized two 

stocks of fin whales in the North 

Pacific: the East China Sea and the 

rest of the North Pacific (Donovan 

1991). Mizroch et al. (1984) cites 

evidence for additional fin whale 

subpopulations in the North Pacific. 

From whaling records, fin whales 

that were marked in winter 1962-70 

off southern California were later 

taken in commercial whaling 

operations between central 

California and the Gulf of Alaska in 

summer (Mizroch et al. 1984). 

More recent observations show 

aggregations of fin whales yearround in southern/central California 

(Dohl et al. 1983; Barlow 1997; 

Forney et al. 1995), year-round in 

the Gulf of California (Tershy et al. 

1993), in summer in Oregon (Green 

et al. 1992; McDonald 1994), and in 

summer/autumn in the Shelikof 

Strait/Gulf of Alaska (Brueggeman 

et al. 1990). Acoustic signals from 

fin whale are detected year-round 

off northern California, Oregon and 

Washington, with a concentration of 

vocal activity between September 

and February (Moore et al. 1998). Fin 

whales appear very scarce in the eastern 

tropical Pacific in summer (Wade and 

Gerrodette 1993) and winter (Lee 

1993). 

OREGON

WASHINGTON

CALIFORNIA

 There is still insufficient 

information to accurately determine 

population structure, but from a 

conservation perspective it may be risky to assume panmixia in the entire North Pacific. In the North 

Atlantic, fin whales were locally depleted in some feeding areas by commercial whaling (Mizroch et al. 

1984), in part because subpopulations were not recognized. This assessment will cover the stock of fin 

whales which is found along the coasts of California, Oregon, and Washington. Because fin whale 

abundance appears lower in winter/spring in California (Dohl et al. 1983; Forney et al. 1995) and in Oregon 

(Green et al. 1992), it is likely that the distribution of this stock extends seasonally outside these coastal 

waters. Genetic studies of the fin whales have shown that the population in the Gulf of California is 

isolated from fin whales in the rest of the eastern North Pacific and is an evolutionary unique population 

(Bérubé et al. 2002). The Marine Mammal Protection Act (MMPA) stock assessment reports recognize 

three stocks of fin whales in the North Pacific: 1) the California/Oregon/Washington stock (this report), 2) 

the Hawaii stock, and 3) the Alaska stock. 

Figure 1. Fin whale sighting locations based on aerial 

and shipboard surveys off California, Oregon, and 

Washington, 1991-2005 (see Appendix 2 for data 

sources and information on timing and location of 

surveys). Dashed line represents the U.S. EEZ; thin 

lines indicate completed transect effort of all surveys 

combined. 

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

45°0'0"N

40°0'0"N

182
POPULATION SIZE

 The initial pre-whaling population of fin whales in the North Pacific was estimated to be 42,000-

45,000 (Ohsumi and Wada 1974). In 1973, the North Pacific population was estimated to have been 

reduced to 13,620-18,680 (Ohsumi and Wada 1974), of which 8,520-10,970 were estimated to belong to 

the eastern Pacific stock. A minimum of 148 individually-identified fin whales are found in the Gulf of 

California (Tershy et al. 1990). Recently 3,279 (CV = 0.31) fin whales were estimated to be off California, 

Oregon and Washington based on ship surveys in summer/autumn of 1996 (Barlow and Taylor 2001) and 

2001 (Barlow 2003). A 2005 ship survey of the same area resulted in an abundance estimate of 3,281 

(CV=0.25) fin whales (Forney 2007). The best estimate of fin whale abundance in California, Oregon, and 

Washington waters out to 300 nmi is the geometric mean of line transect estimates from summer/autumn 

ship surveys conducted in 2001 (Barlow 2003) and 2005 (Forney 2007), or 3,454 (CV = 0.27) whales. This 

is probably an underestimate because it almost certainly excludes some fin whales which could not be 

identified in the field and which were recorded as “unidentified rorqual” or “unidentified large whale”. 

Minimum Population Estimate

 The minimum population estimate for fin whales is taken as the lower 20th percentile of the lognormal distribution of abundance estimated from 2001 and 2005 summer/fall ship surveys (Barlow 2003; 

Forney 2007) or approximately 2,760. 

Current Population Trend

 There is some indication that fin whales have increased in abundance in California coastal waters 

between 1979/80 and 1991 (Barlow 1994) and between 1991 and 1996 (Barlow 1997), but these trends are 

not significant. Although the population in the North Pacific is expected to have grown since receiving 

protected status in 1976, the possible effects of continued unauthorized take (Yablokov 1994) and 

incidental ship strikes and gillnet mortality make this uncertain. There is no evidence of a population trend 

from recent line-transect abundance surveys conducted in 1996, 2001, and 2005 in California, Oregon, and 

Washington waters out to 300 nmi. Estimates from these three surveys have been 2,921 (CV=0.31); 3,636 

(CV=0.50); and 3,281 (CV=0.25) whales, respectively (Barlow 2003; Forney 2007). 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 There are no estimates of the growth rate of fin whale populations in the North Pacific (Best 

1993). 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum 

population size ( 2,760) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times

a recovery factor of 0.3 (for an endangered species, with Nmin > 1,500 and CVNmin < 0.50), resulting in a 

PBR of 16. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Historic Whaling

 Approximately 46,000 fin whales were taken from the North Pacific by commercial whalers 

between 1947 and 1987 (C. Allison, IWC, pers. comm.), including 1,060 fin whales taken by coastal 

whalers in central California between 1958 and 1965 (Rice 1974). In addition, approximately 3,800 were 

taken off the west coast of North America between 1919 and 1929 (Tonnessen and Johnsen 1982), and 177 

were taken by coastal whalers off California between 1919 and 1926 (Clapham et al. 1997). Fin whales in 

the North Pacific were given protected status by the IWC in 1976. 

Fisheries Information

 The offshore drift gillnet fishery is the only fishery that is likely to take fin whales from this stock, 

and one fin whale death has been observed since 1990 when NMFS began observing the fishery . Detailed 

information on this fishery is provided in Appendix 1. After the 1997 implementation of a Take Reduction 

Plan, which included skipper education workshops and required the use of pingers and minimum 6-fathom 

extenders, overall cetacean entanglement rates in the drift gillnet fishery dropped considerably (Barlow and 

Cameron 2003). Mean annual takes for this fishery (Table 1) are based on 2000-2004 data. This results in 

183
an average estimate of zero fin whales taken annually. Some gillnet mortality of large whales may go 

unobserved because whales swim away with a portion of the net; however, fishermen report that large 

rorquals (blue and fin whales) usually swim through nets without entangling and with very little damage to 

the nets. 

 Drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of Baja 

California, Mexico and may take animals from this population. Quantitative data are available only for the 

Mexican swordfish drift gillnet fishery, which uses vessels, gear, and operational procedures similar to 

those in the U.S. drift gillnet fishery, although nets may be up to 4.5 km long (Holts and Sosa-Nishizaki 

1998). The fleet increased from two vessels in 1986 to 31 vessels in 1993 (Holts and Sosa-Nishizaki 1998). 

The total number of sets in this fishery in 1992 can be estimated from data provided by these authors to be 

approximately 2700, with an observed rate of marine mammal bycatch of 0.13 animals per set (10 marine 

mammals in 77 observed sets; Sosa-Nishizaki et al. 1993). This overall mortality rate is similar to that 

observed in California driftnet fisheries during 1990-95 (0.14 marine mammals per set; Julian and Beeson, 

1998), but species-specific information is not available for the Mexican fisheries. Previous efforts to 

convert the Mexican swordfish driftnet fishery to a longline fishery have resulted in a mixed-fishery, with 

20 vessels alternately using longlines or driftnets, 23 using driftnets only, 22 using longlines only, and 

seven with unknown gear type (Berdegué 2002). 

Table 1. Summary of available information on the incidental mortality and injury of fin whales 

(CA/OR/WA stock) for commercial fisheries that might take this species (Carretta and Chivers 2004, 

Carretta et al. 2005a, 2005b). 

Fishery Name Year(s) Data Type 

Percent 

Observer 

Coverage 

Observed 

mortality (and 

injury in 

parentheses) 

Estimated 

mortality (CV 

in 

parentheses) 

Mean annual 

takes (CV in 

parentheses) 

CA/OR thresher 

shark/swordfish 

drift gillnet fishery 

2000 

2001 

2002 

2003 

2004 

observer 

22.9% 

20.4% 

22.1% 

20.2% 

20.6% 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0 (n/a) 

Total annual takes 0 (n/a) 

Ship Strikes

 Ship strikes were implicated in the deaths of six fin whales and the injury of another from 2000-

2004 NMFS, unpublished stranding data). During 2000-2004, there were an additional five injuries and 

three mortalities of unidentified large whales attributed to ship strikes. Additional mortality from ship 

strikes probably goes unreported because the whales do not strand or, if they do, they do not always have 

obvious signs of trauma. The average observed annual mortality and injury due to ship strikes is 1.4 fin 

whales per year during 2000-2004. 

STATUS OF STOCK

 Fin whales in the entire North Pacific were estimated to be at less than 38% (16,625 out of 43,500) 

of historic carrying capacity (Mizroch et al. 1984). The initial abundance has never been estimated 

separately for the "west coast" stock, but this stock was also probably depleted by whaling. Fin whales are 

formally listed as "endangered" under the Endangered Species Act (ESA), and consequently the California 

to Washington stock is automatically considered as a "depleted" and "strategic" stock under the MMPA. 

The total incidental mortality due to fisheries (zero) and ship strikes (1.4/yr) is less than the calculated PBR 

(16). Total fishery mortality is less than 10% of PBR and, therefore, may be approaching zero mortality 

and serious injury rate. There is some indication that the population may be growing. Increasing levels of 

anthropogenic sound in the world’s oceans has been suggested to be a habitat concern for whales, 

particularly for baleen whales that may communicate using low-frequency sound (Croll et al. 2002). 

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186
Revised 10/30/2007 

BRYDE'S WHALE (Balaenoptera edeni): Eastern Tropical Pacific 

Stock 

STOCK DEFINITION AND 

GEOGRAPHIC RANGE

 The International Whaling 

Commission (IWC) recognizes 3 

stocks of Bryde's whales in the North 

Pacific (eastern, western, and East 

China Sea), 3 stocks in the South 

Pacific (eastern, western and 

Solomon Islands), and one crossequatorial stock (Peruvian) (Donovan 

1991). Bryde's whales are distributed 

widely across the tropical and warmtemperate Pacific (Leatherwood et al. 

1982), and there is no real 

justification for splitting stocks 

between the northern and southern 

hemispheres (Donovan 1991). 

Recent surveys (Lee 1993; Wade and 

Gerrodette 1993) have shown them to 

be common and distributed 

throughout the eastern tropical Pacific 

with a concentration around the 

equator east of 110o

W (corresponding 

approximately to the IWC's "Peruvian 

stock") and a reduction west of 

140o

W. They are also the most 

common baleen whale in the central 

Gulf of California (Tershy et al. 

1990). Only one was positively 

identified in surveys of California 

coastal waters (Barlow 1997). 

Bryde's whales in California are likely to 

belong to a larger population inhabiting at 

least the eastern part of the tropical Pacific. 

For the Marine Mammal Protection Act 

(MMPA) stock assessment reports, Bryde's 

whales within the Pacific U.S. Exclusive 

Economic Zone are divided into two areas: 

1) the eastern tropical Pacific (east of 150o

W 

and including the Gulf of California and waters off California; this report), and 2) Hawaiian waters. 

OREGON

WASHINGTON

CALIFORNIA

POPULATION SIZE

 North Pacific, Bryde's whale abundance in the early 1980s was estimated 

depend

 In the western

in ently by tag mark-recapture and ship survey methods to be 22,000 to 24,000 (Tillman and 

Mizroch 1982; Miyashita 1986). Bryde's whale abundance has never been estimated for the entire eastern 

Pacific; however, a portion of that stock in the eastern tropical Pacific was estimated recently as 13,000 

(CV=0.20; 95% C.I.=8,900-19,900) (Wade and Gerrodette 1993), and the minimum number in the Gulf of 

California is 160 based on individually-identified whales (Tershy et al. 1990). Only one confirmed sighting 

of Bryde's whales and five possible sightings (identified as sei or Bryde's whales) were made in California 

Figure 1. Sighting locations of Bryde’s whales 

based on aerial and shipboard surveys off 

California, Oregon, and Washington, 1991- 2005 

(see Appendix 2 for data sources and information 

on timing and location of surveys). Dashed line 

represents the U.S. EEZ; thin lines indicate 

completed transect effort of all surveys combined. 

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

45°0'0"N

40°0'0"N

187
waters during extensive ship and aerial surveys between 1991 and 2005 (Barlow 2003b; Hill and Barlow 

1992; Carretta and Forney 1993; Forney 2007; Mangels and Gerrodette 1994; VonSaunder and Barlow 

1999). Green et al. (1992) did not report any sightings of Bryde's whales in aerial surveys off Oregon and 

Washington. The only sighting of Bryde’s whale in this region occurred during a survey over 10 years ago, 

thus, there is no current estimate of abundance for California, Oregon, and Washington waters. 

Minimum Population Estimate

ate of Bryde’s whale abundance for the eastern tropical Pacific (11,163; 

ade an

urrent Population Trend

 trends in Bryde's whale abundance in the eastern tropical Pacific. 

URRENT AND MAXIMUM NET PRODUCTIVITY RATES

opulations in the Pacific (Best 1993). 

OTENTIAL BIOLOGICAL REMOVAL

R) level for this stock cannot be calculated because the only 

levant

UMAN CAUSED MORTALITY

d take of North Pacific Bryde's whales by commercial whalers totaled 15,076 in the 

estern 

able 1. Summary of available information on the incidental mortality and injury of Bryde’s whales 

Fishery Name Year(s) Data Type 

Percent Observed 

m

Estimated 

m

Mean annual 

 The only minimum estim

W d Gerrodette 1993) is over 8 years old and thus, no current estimate of minimum abundance is 

available. 

C

 There are no data on

C

 There are no estimates of the growth rate of Bryde's whale p

P

 The potential biological removal (PB

re abundance estimate (Wade and Gerrodette 1993) is more than 8 years old. Additional data on the 

abundance of Bryde’s whales in the eastern Pacific was collected during line transect ship surveys between 

1998 and 2006 but abundance estimates are currently unavailable. 

H

Historic Whaling 

 The reporte

w Pacific from 1946-1983 (Holt 1986) and 2,873 in the eastern Pacific from 1973-81 (Cooke 1983). 

In addition, 2,304 sei-or-Bryde's whales were taken in the eastern Pacific from 1968-72 (Cooke 1983) 

(based on subsequent catches, most of these were probably Bryde's whales). None were reported taken by 

shore-based whaling stations in central or northern California between 1919 and 1926 (Clapham et al. 

1997) or 1958 and 1965 (Rice 1974). There has been a prohibition on taking Bryde's whales since 1988. 

T

(eastern tropical Pacific stock) for commercial fisheries that might take this species (Julian 1997; Julian and 

Beeson 1998; Cameron and Forney 1999). n/a indicates that data are not available. Mean annual takes are 

based on 1994-98 data unless noted otherwise. 

Observer 

Coverage 

ortality (and

injury in 

parentheses) 

ortality (CV

in 

parentheses) 

takes (CV in 

parentheses) 

CA/OR thresher 

d

shark/swordfish 2000-2004 observer 20-23% 0 

rift gillnet fishery 

0,0,0,0,0 0,0,0,0,0 

Mexico thresher 

shark/swordfish 

drift gillnet fishery 

1991-95 observer n/a n/a n/a n/a 

Total annual takes 0 

ishery Information 

rift gillnet fishery is the only fishery that is likely to take Bryde’s whales from this 

ock, bu

F

 The offshore d

st t no fishery mortalities or serious injuries have been observed (Table 1). Detailed information on 

this fishery is provided in Appendix 1. After the 1997 implementation of a Take Reduction Plan, which 

included skipper education workshops and required the use of pingers and minimum 6-fathom extenders, 

overall cetacean entanglement rates in the drift gillnet fishery dropped considerably (Barlow and Cameron 

2003a). Mean annual takes for this fishery (Table 1) are based on 2000-2004 data. This results in an 

average estimate of zero Bryde’s whales taken annually. However, some gillnet mortality of large whales 

may go unobserved because whales swim away with a portion of the net. 

188
 Drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of Baja 

California and may take animals from this population. Quantitative data are available only for the Mexican 

swordfish drift gillnet fishery, which uses vessels, gear, and operational procedures similar to those in the 

U.S. drift gillnet fishery, although nets may be up to 4.5 km long (Holts and Sosa-Nishizaki 1998). The 

fleet increased from two vessels in 1986 to 31 vessels in 1993 (Holts and Sosa-Nishizaki 1998). The total 

number of sets in this fishery in 1992 can be estimated from data provided by these authors to be 

approximately 2,700, with an observed rate of marine mammal bycatch of 0.13 animals per set (10 marine 

mammals in 77 observed sets; Sosa-Nishizaki et al. 1993). This overall mortality rate is similar to that 

observed in California driftnet fisheries during 1990-95 (0.14 marine mammals per set; Julian and Beeson 

1998), but species-specific information is not available for the Mexican fisheries. Previous efforts to 

convert the Mexican swordfish driftnet fishery to a longline fishery have resulted in a mixed fishery, with 

20 vessels alternately using longlines or driftnets, 23 using driftnets only, 22 using longlines only, and 

seven with unknown gear type (Berdegué 2002). 

Ship Strikes 

Ship strikes may occasionally kill Bryde's whales as they are known to kill their larger relatives: 

blue and fin whales. No ship strikes have been reported for this species in this area. During 2000-2004, 

there were five injuries and three mortalities of unidentified large whales attributed to ship strikes, but it is 

unlikely that any of these were Bryde’s whales. 

STATUS OF STOCK

 Commercial whaling of Bryde's whales was largely limited to the western Pacific. Bryde's whales 

are not listed as "threatened" or "endangered" under the Endangered Species Act (ESA). Bryde's whales in 

the eastern tropical Pacific would not be considered a strategic stock under the MMPA. The total humancaused mortality rate is estimated to be zero; therefore, under the MMPA, total fishery mortality is 

approaching zero mortality and serious injury rate. Increasing levels of anthropogenic sound in the world’s 

oceans has been suggested to be a habitat concern for whales, particularly for baleen whales that may 

communicate using low-frequency sound. 

REFERENCES

Barlow, J. 1997. Preliminary estimates of cetacean abundance off California, Oregon, and Washington 

based on a 1996 ship survey and comparisons of passing and closing modes. Admin. Rept. LJ-97-

11 available from Southwest Fisheries Science Center, P.O. Box 271, La Jolla, CA. 25pp. 

Barlow, J., R. W. Baird, J. E. Heyning, K. Wynne, A. M. Manville, II, L. F. Lowry, D. Hanan, J. Sease, and 

V. N. Burkanov. 1994. A review of cetacean and pinniped mortality in coastal fisheries along the 

west coast of the U.S. and Canada and the east coast of the Russian Federation. Rep. Int. Whal. 

Commn, Special Issue 15:405-425. 

Barlow, J. and G. A. Cameron. 2003a. Field experiments show that acoustic pingers reduce marine 

mammal bycatch in the California drift gillnet fishery. Marine Mammal Science 19(2):265-283. 

Barlow, J. 2003b. Preliminary estimates of the abundance of cetaceans along the U.S. west coast: 

1991_2001. Southwest Fisheries Science Center Administrative Report LJ_03_03. Available 

from SWFSC, 8604 La Jolla Shores Dr., La Jolla CA 92037. 31p. 

Berdegué, J. 2002. Depredación de las especies pelágicas reservadas a la pesca deportiva y especies en 

peligro de extinción con uso indiscriminado de artes de pesca no selectivas (palangres, FAD's, 

trampas para peces y redes de agallar fijas y a la deriva) por la flota palangrera Mexicana. 

Fundación para la conservación de los picudos. A.C. Mazatlán, Sinaloa, 21 de septiembre. 

Best, P. B. 1993. Increase rates in severely depleted stocks of baleen whales. ICES J. Mar. Sci. 50:169-

186. 

Cameron, G. A. and K. A. Forney. 1999. Preliminary estimates of cetacean mortality in the California 

gillnet fisheries for 1997 and 1998. Paper SC/51/O4 presented to the International Whaling 

Commission, May 1999 (unpublished). 14 pp. 

Carretta, J. V. and K. A. Forney. 1993. Report on two aerial surveys for marine mammals in California 

coastal waters utilizing a NOAA DeHavilland Twin Otter Aircraft: March 9-April7, 1991 and 

February 8-April 6, 1992. NOAA Tech. Memo. NOAA-TM-NMFS-SWFSC-185. 77pp. 

189
Clapham, P. J., S. Leatherwood, I. Szczepaniak, and R. L. Brownell, Jr. 1997. Catches of humpback and 

other whales from shore stations at Moss Landing and Trinidad, California, 1919-1926. Mar. 

Mamm. Sci. 13(3):368-394. 

Cooke, J. G. 1983. Estimates of the stock of Bryde's whales fished off the coast of Peru. Rept. Int. Whal. 

Commn. 33:453-456. 

Donovan, G. P. 1991. A review of IWC stock boundaries. Rept. Int. Whal. Commn., Special Issue 13:39-

68. 

Forney, K.A. 2007. Preliminary estimates of cetacean abundance along the U.S. west coast and within 

four National Marine Sanctuaries during 2005. U.S. Department of Commerce, NOAA Technical 

Memorandum NMFS-SWFSC-406. 27p. 

Green, G. A., J. J. Brueggeman, R. A. Grotefendt, C. E. Bowlby, M. L. Bonnell, K. C. Balcomb, III. 1992. 

Cetacean distribution and abundance off Oregon and Washington, 1989-1990. Ch. 1 In: J. J. 

Brueggeman (ed.). Oregon and Washington Marine Mammal and Seabird Surveys. Minerals 

Management Service Contract Report 14-12-0001-30426. 

Hanan, D. A. 1986. California Department of Fish and Game coastal marine mammal study, annual report 

for the period July 1, 1983 - June 30, 1984. Admin. Rept. LJ-86-16 available from Southwest 

Fisheries Science Center, P.O. Box 271, La Jolla, CA. 55pp. 

Hanan, D. A., D. B. Holts, and A. L. Coan, Jr. 1993. The California drift gill net fishery for sharks and 

swordfish, 1981-82 through 1990-91. Calif. Dept. Fish and Game Fish. Bull. No. 175. 95pp. 

Heyning, J. E., and T. D. Lewis. 1990. Fisheries interactions involving baleen whales off southern 

California. Rep. int. Whal. Commn. 40:427-431. 

Hill, P. S. and J. Barlow. 1992. Report of a marine mammal survey of the California coast aboard the 

research vessel McARTHUR July 28-November 5, 1991. NOAA Technical Memorandum 

NOAA-TM-NMFS-SWFSC-169. NTIS #PB93-109908. 103pp. 

Holt, S. 1986. Aspects of the assessment and regulation of Bryde's whales in the Northwest Pacific. Rept. 

Int. Whal. Commn. 36:257-262. 

Holts, D. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La Jolla, 

CA 92038. 

Holts, D. and O. Sosa-Nishizaki. 1998. Swordfish, Xiphias gladius, fisheries of the eastern North Pacific 

Ocean. In: I. Barrett, O. Sosa-Nishizaki and N. Bartoo (eds.). Biology and fisheries of swordfish, 

Xiphias gladius. Papers from the International Symposium on Pacific Swordfish, Ensenada 

Mexico, 11-14 December 1994. U.S. Dep. Commer., NOAA Tech. Rep. NMFS 142, 276 p. 

Julian, F. 1997. Cetacean mortality in the California gill net fisheries: preliminary estimates for 1996. 

Paper SC/49/SM2 presented to the International Whaling Commission, September 1997 

(unpublished). 13pp. 

Julian, F. and M. Beeson. 1998. Estimates for marine mammal, turtle, and seabird mortality for two 

California gillnet fisheries: 1990-95. Fish. Bull. 96:271-284. 

Leatherwood, S., R. R. Reeves, W. F. Perrin, and W. E. Evans. 1982. Whales, dolphins, and porpoises of 

the eastern North Pacific and adjacent Arctic waters: A guide to their identification. NOAA 

Technical Rept. NMFS Circular 444. 245 pp. 

Lee, T. 1993. Summary of cetacean survey data collected between the years of 1974 and 1985. NOAA 

Tech. Memo. NOAA-TM-NMFS-SWFSC-181. 184 pp. 

Mangels, K. F. and T. Gerrodette. Report of cetacean sightings during a marine mammal survey in the 

eastern Pacific Ocean and the Gulf of California aboard the NOAA ships McArthur and David 

Starr Jordan July 28 - November 6, 1993. U.S. Dep. Commer. NOAA Tech. Memo. NMFSSWFSC-221. 88 pp. 

Miyashita, T. 1986. Sighting estimate for the Bryde's whale stock in the western North Pacific. Rept. Int. 

Whal. Commn. 36:249-252. 

Rice, D. W. 1974. Whales and whale research in the eastern North Pacific. pp. 170-195 In: W. E. 

Schevill (ed.). The Whale Problem: A Status Report. Harvard Press, Cambridge, MA. 

Sosa-Nishizaki, O., R. De la Rosa Pacheco, R. Castro Longoria, M. Grijalva Chon, and J. De la Rosa 

Velez. 1993. Estudio biologico pesquero del pez (Xiphias gladius) y otras especies de picudos 

(marlins y pez vela). Rep. Int. CICESE, CTECT9306. 

Tershy, B. R., D. Breese, and C. S. Strong. 1990. Abundance, seasonal distribution and population 

composition of balaenopterid whales in the Canal de Ballenas, Gulf of California, Mexico. Rept. 

Int. Whal. Commn., Special Issue 12:369-375. 

190
Tillman, M. F. and S. A. Mizroch. 1982. Mark-recapture estimates of abundance for the western Northern 

Pacific stock of Bryde's whales. Rept. Int. Whal. Commn. 32:335-337. 

Von Saunder, A. and J. Barlow. 1999. A report of the Oregon, California and Washington Line-transect 

Experiment (ORCAWALE) conducted in west coast waters during summer/fall 1996. U.S. Dep. 

Commer. NOAA Tech. Memo. NMFS-SWFSC-264. 40 pp. 

Wade, P. R. and T. Gerrodette. 1993. Estimates of cetacean abundance and distribution in the eastern 

tropical Pacific. Rept. Int. Whal. Commn. 43:477-493. 

191
Revised 10/30/2007 

SEI WHALE (Balaenoptera borealis): Eastern North Pacific Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

 The International Whaling 

Commission (IWC) only considers 

one stock of sei whales in the North 

Pacific (Donovan 1991), but some 

evidence exists for multiple 

populations (Masaki 1977; Mizroch 

et al. 1984; Horwood 1987). Sei 

whales are distributed far out to sea 

in temperate regions of the world 

and do not appear to be associated 

with coastal features. Whaling 

effort for this species was 

distributed continuously across the 

North Pacific between 45-55o

N 

(Masaki 1977). Two sei whales that 

were tagged off California were 

later killed off Washington and 

British Columbia (Rice 1974) and 

the movement of tagged animals has 

been noted in many other regions of 

the North Pacific. Sei whales are 

now rare in California waters (Dohl 

et al. 1983; Barlow 1997; Forney et 

al. 1995; Mangels and Gerrodette 

1994), but were the fourth most 

common whale taken by California 

coastal whalers in the 1950s-1960s 

(Rice 1974). They are extremely 

rare south of California (Wade and 

Gerrodette 1993; Lee 1993). 

Lacking additional information on 

sei whale population structure, sei 

whales in the eastern North Pacific (east 

of longitude 180o

) will be considered as 

a separate stock. 

OREGON

WASHINGTON

CALIFORNIA

POPULATION SIZE

 Ohsumi and Wada (1974) 

estimate the pre-whaling abundance of 

sei whales to be 58,000-62,000 in the North Pacific. Later, Tillman (1977) used a variety of different 

methods to estimate the abundance of sei whales in the North Pacific and revised this pre-whaling estimate 

to 42,000. His estimates for the year 1974 ranged from 7,260 to 12,620. All methods depend on using the 

history of catches and trends in CPUE or sighting rates; there have been no direct estimates of sei whale 

abundance in the entire (or eastern) North Pacific based on sighting surveys. Only five confirmed sightings 

of sei whales were made in California, Oregon, and Washington waters during extensive ship and aerial 

surveys between 1991-2005, (Hill and Barlow 1992; Carretta and Forney 1993; Mangels and Gerrodette 

1994; VonSaunder and Barlow 1999; Barlow 2003; Forney 2007). Green et al. (1992) did not report any 

sightings of sei whales in aerial surveys of Oregon and Washington. Abundance estimates for the two most 

recent line transect surveys of California, Oregon, and Washington waters out to 300 nmi are 25 (CV=1.01) 

and 74 (CV=0.88) sei whales, respectively (Barlow 2003, Forney 2007). The best estimate of abundance 

Figure 1. Sei whale sighting locations based on aerial 

and shipboard surveys off California, Oregon, and 

Washington, 1991-2005 (see Appendix 2 for data 

sources and information on timing and location of 

surveys). Dashed line represents the U.S. EEZ; thin

lines indicate completed transect effort of all surveys 

combined. 

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

45°0'0"N

40°0'0"N

192
for California, Oregon, and Washington waters out to 300 nmi is the unweighted geometric mean of the 

2001 and 2005 estimates, or 43 (CV = 0.61) sei whales (Barlow 2003; Forney 2007). 

Minimum Population Estimate

 The minimum population estimate for sei whales is taken as the lower 20th percentile of the lognormal distribution of abundance estimated from 2001 and 2005 shipboard line-transect surveys, or 

approximately 27. 

Current Population Trend

 There are no data on trends in sei whale abundance in the eastern North Pacific waters. Although 

the population in the North Pacific is expected to have grown since being given protected status in 1976, 

the possible effects of continued unauthorized take (Yablokov 1994) and incidental ship strikes and gillnet 

mortality make this uncertain. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 There are no estimates of the growth rate of sei whale populations in the North Pacific (Best 

1993). 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum 

population size (27) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a 

recovery factor of 0.1 (for an endangered species), resulting in a PBR of 0.05. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Historic Whaling

 The reported take of North Pacific sei whales by commercial whalers totaled 61,500 between 1947 

and 1987 (C. Allison, IWC, pers. comm.). Of these, 384 were taken by-shore-based whaling stations in 

central California between 1958 and 1965 (Rice 1974). An additional 26 were taken off central and 

northern California between 1919 and 1926 (Clapham et al. 1997). There has been an IWC prohibition on 

taking sei whales since 1976, and commercial whaling in the U.S. has been prohibited since 1972. 

Fishery Information

 The offshore drift gillnet fishery is the only fishery that is likely to take sei whales from this stock, 

but no fishery mortalities or serious injuries have been observed (Table 1). Detailed information on this 

fishery is provided in Appendix 1. After the 1997 implementation of a Take Reduction Plan, which 

included skipper education workshops and required the use of pingers and minimum 6-fathom extenders, 

overall cetacean entanglement rates in the drift gillnet fishery dropped considerably (Barlow and Cameron 

2003). Mean annual takes for this fishery (Table 1) are based on 2000-2004 data. This results in an 

average estimate of zero sei whales taken annually. However, some gillnet mortality of large whales may 

go unobserved because whales swim away with a portion of the net. 

Table 1. Summary of available information on the incidental mortality and injury of sei whales (eastern 

North Pacific stock) for commercial fisheries that might take this species. n/a indicates that data are not 

available. Mean annual takes are based on 2000-2004 data unless noted otherwise. 

Fishery Name Year(s) Data Type 

Percent 

Observer 

Coverage 

Observed 

mortality (and 

injury in 

parentheses) 

Estimated 

mortality (CV 

in 

parentheses) 

Mean annual 

takes (CV in 

parentheses) 

CA/OR thresher 

shark/swordfish 

drift gillnet fishery 

2000-2004 Observer 

data 20-23% 0,0,0,0,0 0,0,0,0,0 0 

Total annual takes 0 

193
Ship Strikes 

 One ship strike mortality was reported in Washington in 2003 (NMFS Northwest Regional 

Office, unpublished data). During 2000-2004, there were an additional five injuries and three mortalities of 

unidentified large whales attributed to ship strikes. Additional mortality from ship strikes probably goes 

unreported because the whales do not strand or, if they do, they do not always have obvious signs of 

trauma. The average observed annual mortality due to ship strikes is 0.2 sei whales per year for the period 

2000-2004. 

STATUS OF STOCK

 Previously, sei whales were estimated to have been reduced to 20% (8,600 out of 42,000) of their 

pre-whaling abundance in the North Pacific (Tillman 1977). The initial abundance has never been reported 

separately for the eastern North Pacific stock, but this stock was also probably depleted by whaling. Sei 

whales are formally listed as "endangered" under the Endangered Species Act (ESA), and consequently the 

eastern North Pacific stock is automatically considered as a "depleted" and "strategic" stock under the 

Marine Mammal Protection Act (MMPA). Total estimated fishery mortality is zero and therefore is 

approaching zero mortality and serious injury rate. The total incidental mortality due to ship strikes 

(0.2/yr) is greater than the calculated PBR (0.05). Increasing levels of anthropogenic sound in the world’s 

oceans has been suggested to be a habitat concern for whales, particularly for baleen whales that may 

communicate using low-frequency sound (Croll et al. 2002). 

REFERENCES

Barlow, J. 1997. Preliminary estimates of cetacean abundance off California, Oregon, and Washington 

based on a 1996 ship survey and comparisons of passing and closing modes. Admin. Rept. LJ-97-

11. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA. 25 pp. 

Barlow, J., R. W. Baird, J. E. Heyning, K. Wynne, A. M. Manville, II, L. F. Lowry, D. Hanan, J. Sease, and 

V. N. Burkanov. 1994. A review of cetacean and pinniped mortality in coastal fisheries along the 

west coast of the U.S. and Canada and the east coast of the Russian Federation. Rep. Int. Whal. 

Commn, Special Issue 15:405-425. 

Barlow, J. and G. A. Cameron. 2003. Field experiments show that acoustic pingers reduce marine mammal 

bycatch in the California drift gillnet fishery. Marine Mammal Science 19(2):265-283. 

Barlow, J. 2003. Preliminary estimates of the abundance of cetaceans along the U.S. west coast: 

1991_2001. Southwest Fisheries Science Center Administrative Report LJ_03_03. Available 

from SWFSC, 8604 La Jolla Shores Dr., La Jolla CA 92037. 31p. 

Berdegué, J. 2002. Depredación de las especies pelágicas reservadas a la pesca deportiva y especies en 

peligro de extinción con uso indiscriminado de artes de pesca no selectivas (palangres, FAD's, 

trampas para peces y redes de agallar fijas y a la deriva) por la flota palangrera Mexicana. 

Fundación para la conservación de los picudos. A.C. Mazatlán, Sinaloa, 21 de septiembre. 

Best, P. B. 1993. Increase rates in severely depleted stocks of baleen whales. ICES J. Mar. Sci. 50:169-

186. 

Carretta, J. V. and K. A. Forney. 1993. Report on two aerial surveys for marine mammals in California 

coastal waters utilizing a NOAA DeHavilland Twin Otter Aircraft: March 9-April7, 1991 and 

February 8-April 6, 1992. U.S. Dep. Commer. NOAA Tech. Memo. NMFS-SWFSC-185. 77 pp. 

Carretta, J.V. and S.J. Chivers. 2004. Preliminary estimates of marine mammal mortality and biological 

sampling of cetaceans in California gillnet fisheries for 2003. Paper SC/56/SM1 presented to the 

IWC Scientific Committee, June 2004 (unpublished). [Available from Southwest Fisheries 

Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 

92037, USA]. 

Carretta, J.V., S.J. Chivers, and K. Danil. 2005a. Preliminary estimates of marine mammal bycatch, 

mortality, and biological sampling of cetaceans in California gillnet fisheries for 2004. 

Administrative Report LJ-05-10, available from Southwest Fisheries Science Center, 8604 La 

Jolla Shores Drive, La Jolla, California, 92037. 17 p. 

Carretta, J.V., T. Price, D. Petersen, and R. Read. 2005b. Estimates of marine mammal, sea turtle, and 

seabird mortality in the California drift gillnet fishery for swordfish and thresher shark, 1996-

2002. Marine Fisheries Review 66(2):21-30. 

194
Clapham, P. J., S. Leatherwood, I. Szczepaniak, and R. L. Brownell, Jr. 1997. Catches of humpback and 

other whales from shore stations at Moss Landing and Trinidad, California, 1919-1926. Mar. 

Mamm. Sci. 13(3):368-394. 

Croll, D.A., C.W. Clark, A. Acevedo, B. Tershy, S. Flores, J. Gedamke, and J. Urban. 2002. Only male 

fin whales sing loud songs. Nature 417:809 

Dohl, T. P., R. C. Guess, M. L. Duman, and R. C. Helm. 1983. Cetaceans of central and northern 

California, 1980-83: Status, abundance, and distribution. Final Report to the Minerals 

Management Service, Contract No. 14-12-0001-29090. 284 pp. 

Donovan, G. P. 1991. A review of IWC stock boundaries. Rept. Int. Whal. Commn., Special Issue 13:39-

68. 

Forney, K. A., J. Barlow, and J. V. Carretta. 1995. The abundance of cetaceans in California waters. Part 

II: Aerial surveys in winter and spring of 1991 and 1992. Fish. Bull. 93:15-26. 

Forney, K.A. 2007. Preliminary estimates of cetacean abundance along the U.S. west coast and within 

four National Marine Sanctuaries during 2005. U.S. Department of Commerce NOAA Technical 

Memorandum, NOAA-TM-NMFS-SWFSC-406. 27p. 

Green, G. A., J. J. Brueggeman, R. A. Grotefendt, C. E. Bowlby, M. L. Bonnell, K. C. Balcomb, III. 1992. 

Cetacean distribution and abundance off Oregon and Washington, 1989-1990. Ch. 1 In: J. J. 

Brueggeman (ed.). Oregon and Washington Marine Mammal and Seabird Surveys. Minerals 

Management Service Contract Report 14-12-0001-30426. 

Hanan, D. A. 1986. California Department of Fish and Game coastal marine mammal study, annual report 

for the period July 1, 1983 - June 30, 1984. Admin. Rept. LJ-86-16. Southwest Fisheries Science 

Center, National Marine Fisheries Service, P.O. Box 271, La Jolla, CA. 55pp. 

Hanan, D. A., D. B. Holts, and A. L. Coan, Jr. 1993. The California drift gill net fishery for sharks and 

swordfish, 1981-82 through 1990-91. Calif. Dept. Fish and Game Fish. Bull. No. 175. 95pp. 

Heyning, J. E., and T. D. Lewis. 1990. Fisheries interactions involving baleen whales off southern 

California. Rep. Int. Whal. Commn. 40:427-431. 

Hill, P. S. and J. Barlow. 1992. Report of a marine mammal survey of the California coast aboard the 

research vessel McARTHUR July 28-November 5, 1991. U.S. Dep. Commer. NOAA Tech. 

Memo. NMFS-SWFSC-169. 103 pp. 

Holts, D. and O. Sosa-Nishizaki. 1998. Swordfish, Xiphias gladius, fisheries of the eastern North Pacific 

Ocean. In: I. Barrett, O. Sosa-Nishizaki and N. Bartoo (eds.). Biology and fisheries of swordfish, 

Xiphias gladius. Papers from the International Symposium on Pacific Swordfish, Ensenada 

Mexico, 11-14 December 1994. U.S. Dep. Commer., NOAA Tech. Rep. NMFS 142, 276 p. 

Horwood, J. 1987. The Sei Whale: Population Biology, Ecology and Management. Croom Helm, 

London, U.K. 375pp. 

Lee, T. 1993. Summary of cetacean survey data collected between the years of 1974 and 1985. U.S. Dep. 

Commer. NOAA Tech. Memo. NMFS-SWFSC-181. 184 pp. 

Mangels, K. F. and T. Gerrodette. Report of cetacean sightings during a marine mammal survey in the 

eastern Pacific Ocean and the Gulf of California aboard the NOAA ships McArthur and David 

Starr Jordan July 28 - November 6, 1993. U.S. Dep. Commer. NOAA Tech. Memo. NMFSSWFSC-221. 88 pp. 

Masaki, Y. 1977. The separation of the stock units of sei whales in the North Pacific. Rept. Int. Whal. 

Commn., Special Issue 1:71-77. 

Mizroch, S. A., D. W. Rice, and J. M. Breiwick. 1984. The sei whale, Balaenoptera borealis. Mar. Fish. 

Rev. 46:25-29. 

Ohsumi, S. and S. Wada. 1974. Status of whale stocks in the North Pacific, 1972. Rept. Int. Whal. 

Commn. 25:114-126. 

Rice, D. W. 1974. Whales and whale research in the eastern North Pacific. pp. 170-195 In: W. E. 

Schevill (ed.). The Whale Problem: A Status Report. Harvard Press, Cambridge, MA. 

Tillman, M. F. 1977. Estimates of population size for the North Pacific sei whale. Rept. Int. Whal. 

Commn., Special Issue 1:98-106. 

Von Saunder, A. and J. Barlow. 1999. A report of the Oregon, California and Washington Line-transect 

Experiment (ORCAWALE) conducted in west coast waters during summer/fall 1996. U.S. Dep. 

Commer. NOAA Tech. Memo. NMFS-SWFSC-264. 40 pp. 

Wade, P. R. and T. Gerrodette. 1993. Estimates of cetacean abundance and distribution in the eastern 

tropical Pacific. Rept. Int. Whal. Commn. 43:477-493. 

195
Yablokov, A. V. 1994. Validity of whaling data. Nature 367:108. 

196
Revised 10/30/2007 

MINKE WHALE (Balaenoptera acutorostrata): 

California/Oregon/Washington Stock 

STOCK DEFINITION AND 

GEOGRAPHIC RANGE

 The International Whaling 

Commission (IWC) recognizes 3 

stocks of minke whales in the North 

Pacific: one in the Sea of 

Japan/East China Sea, one in the 

rest of the western Pacific west of 

180o

N, and one in the "remainder" 

of the Pacific (Donovan 1991). The 

"remainder" stock only reflects the 

lack of exploitation in the eastern 

Pacific and does not imply that only 

one population exists in that area 

(Donovan 1991). In the 

"remainder" area, minke whales are 

relatively common in the Bering and 

Chukchi seas and in the Gulf of 

Alaska, but are not considered 

abundant in any other part of the 

eastern Pacific (Leatherwood et al. 

1982; Brueggeman et al. 1990). In 

the Pacific, minke whales are 

usually seen over continental 

shelves (Brueggeman et al. 1990). 

In the extreme north, minke whales 

are believed to be migratory, but in 

inland waters of Washington and in 

central California they appear to 

establish home ranges (Dorsey et al. 

1990). Minke whales occur yearround in California (Dohl et al. 1983; 

Forney et al. 1995; Barlow 1997) and in 

the Gulf of California (Tershy et al. 

1990). Minke whales are present at 

least in summer/fall along the Baja 

California peninsula (Wade and 

Gerrodette 1993). Because the 

"resident" minke whales from California to Washington appear behaviorally distinct from migratory whales 

further north, minke whales in coastal waters of California, Oregon, and Washington (including Puget 

Sound) are considered as a separate stock. Minke whales in Alaskan waters are considered in a separate 

stock assessment report. 

OREGON

WASHINGTON

CALIFORNIA

POPULATION SIZE

 No estimates have been made for the number of minke whales in the entire North Pacific. The 

number of minke whales off California Oregon, and Washington is estimated to be 898 (CV = 0.65), 

based on ship line transect surveys conducted in summer and autumn of 2001 and 2005 (Barlow 2003; 

Forney 2007). Two minke whales were seen during 1996 aerial surveys in Washington and British 

Columbia inland waters (Calambokidis et al. 1997), but no abundance estimates are available for this area. 

Figure 1. Minke whale sighting locations based on 

aerial and shipboard surveys off California, Oregon, 

and Washington, 1991- 2005 (see Appendix 2 for data 

sources and information on timing and location of 

surveys). Dashed line represents the U.S. EEZ; thin 

lines indicate completed transect effort of all surveys 

combined. 

130°0'0"W 125°0'0"W 120°0'0"W

30°0'0"N

35°0'0"N

45°0'0"N

40°0'0"N

197
Minimum Population Estimate

 The minimum population estimate for minke whales is taken as the lower 20th percentile of the 

log-normal distribution of abundance estimated from 2001 and 2005 summer/fall ship surveys in 

California, Oregon, and Washington waters (Barlow 2003; Forney 2007) or approximately 544. 

Current Population Trend

 There are no data on trends in minke whale abundance in waters of California, Oregon and/or 

Washington. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 There are no estimates of the growth rate of minke whale populations in the North Pacific (Best 

1993). 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum 

population size ( 544) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a 

recovery factor of 0.5 (for a stock of unknown status), resulting in a PBR of 5.4. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Historic Whaling 

 The estimated take of western North Pacific minke whales by commercial whalers was 

approximately 31,000 from 1930 to 1987 (C. Allison, IWC, pers. comm.). Minke whales were not 

harvested commercially in the eastern North Pacific: none were reported taken by shore-based whaling 

stations in central or northern California between 1919 and 1926 (Clapham et al. 1997) or between 1958 

and 1965 (Rice 1974). Reported aboriginal takes of minke whales in Alaska totaled 7 between 1930 and 

1987 (C. Allison, IWC, pers. comm.). 

Table 1. Summary of available information on the incidental mortality and injury of minke whales 

(CA/OR/WA stock) for commercial fisheries that might take this species (Pierce et al. 1996; Cameron and 

Forney 1999, 2000; Carretta 2001, 2002). Mean annual takes are based on 2000-2004 data unless noted 

otherwise. 

Fishery Name Year(s) Data Type 

Percent 

Observer 

Coverage 

Observed 

mortality (and 

injury in 

parentheses) 

Estimated 

mortality (CV 

in 

parentheses) 

Mean annual 

takes (CV in 

parentheses) 

CA/OR thresher 

shark/swordfish 

drift gillnet fishery 

2000 

2001 

2002 

2003 

2004 

observer 

22.9% 

20.4% 

22.1% 

20.2% 

20.6% 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0 

0 

WA Puget Sound 

Region salmon 

drift gillnet fishery 

(areas 7 and 7A) 

2000-

2004 Self-reports 0% 0 0 n/a 

CA angel 

shark/halibut and 

other species large 

mesh (>3.5”) set 

gillnet fishery 

2000 

2001 

2002 

2003 

2004 

1.8%1

0% 

0% 

0% 

0% 

0 0 n/a 

Total annual takes 0 1

In 1999/2000 approximately 25% of the Monterey Bay portion of this fishery was observed, accounting 

for less than 5% of all fishing effort. 

Fishery Information

 Minke whales may occasionally be caught in coastal set gillnets off California, in salmon drift 

gillnet in Puget Sound, Washington, and in offshore drift gillnets off California and Oregon. A summary of 

known fishery mortality and injury for this stock of minke whales is given in Table 1 for the period 2000-

2004. Detailed information on this fishery is provided in Appendix 1. After the 1997 implementation of a 

198
Take Reduction Plan, which included skipper education workshops and required the use of pingers and 

minimum 6-fathom extenders, overall cetacean entanglement rates in the drift gillnet fishery dropped 

considerably (Barlow and Cameron 2003). Mean annual takes for this fishery (Table 1) are based on 

2000-2004 data (Carretta and Chivers 2004, Carretta et al. 2005a, 2005b). This results in an average 

estimate of zero minke whales taken annually. In 1999, a whale skin sample was retrieved from a large 

hole that had been punched through a drift gillnet (trip DN-SD-0941). The sample was later identified as a 

minke whale using genetic sequencing methods. Total fishery mortality for minke whales was not 

estimated for the 1980-86 California Department of Fish and Game observer program for the drift gillnet 

fishery, but based on the 2 observed deaths in 1% of the total sets, the total mortality during this time may 

have been on the order of 200 minke whales or 40 per year. 

 Drift gillnet fisheries for swordfish and sharks exist along the entire Pacific coast of Baja 

California, Mexico and may take animals from this population. Quantitative data are available only for the 

Mexican swordfish drift gillnet fishery, which uses vessels, gear, and operational procedures similar to 

those in the U.S. drift gillnet fishery, although nets may be up to 4.5 km long (Holts and Sosa-Nishizaki 

1998). The fleet increased from two vessels in 1986 to 31 vessels in 1993 (Holts and Sosa-Nishizaki 1998). 

The total number of sets in this fishery in 1992 can be estimated from data provided by these authors to be 

approximately 2700, with an observed rate of marine mammal bycatch of 0.13 animals per set (10 marine 

mammals in 77 observed sets; Sosa-Nishizaki et al. 1993). This overall mortality rate is similar to that 

observed in California driftnet fisheries during 1990-95 (0.14 marine mammals per set; Julian and Beeson, 

1998), but species-specific information is not available for the Mexican fisheries. Previous efforts to 

convert the Mexican swordfish driftnet fishery to a longline fishery have resulted in a mixed-fishery, with 

20 vessels alternately using longlines or driftnets, 23 using driftnets only, 22 using longlines only, and 

seven with unknown gear type (Berdegué 2002). 

Ship Strikes

 Ship strikes were implicated in the death of one minke whale in 1977 (J. Heyning and J. Cordaro, 

pers. comm.). The reported minke whale mortality due to ship strikes is zero for the period 2000-2004. 

Additional mortality from ship strikes probably goes unreported because the whales do not strand or, if they 

do, they do not always have obvious signs of trauma. 

STATUS OF STOCK

 There were no known commercial whaling harvests of minke whales from Baja California to 

Washington. Minke whales are not listed as "endangered" under the Endangered Species Act and are not 

considered "depleted" under the MMPA. The greatest uncertainty in their status is whether entanglement in 

commercial gillnets and ship strikes could have reduced this relatively small population. Because of this, 

the status of the west-coast stock should be considered "unknown". The annual mortality due to fisheries 

(0.0/yr) and ship strikes (0.0/yr) is less than the calculated PBR for this stock (5.4), so they are not 

considered a "strategic" stock under the MMPA. Fishery mortality is less than 10% of the PBR; therefore, 

total fishery mortality is approaching zero mortality and serious injury rate. There is no information on 

trends in the abundance of this stock. Increasing levels of anthropogenic sound in the world’s oceans has 

been suggested to be a habitat concern for whales, particularly for baleen whales that may communicate 

using low-frequency sound. 

REFERENCES

Barlow, J. 1997. Preliminary estimates of cetacean abundance off California, Oregon, and Washington 

based on a 1996 ship survey and comparisons of passing and closing modes. Admin. Rep. LJ-97-

11. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 25 pp. 

Barlow, J., K. A. Forney, P. S. Hill, R. L. Brownell, Jr., J. V. Carretta, D. P. DeMaster, F. Julian, M. S. 

Lowry, T. Ragen, and R. R. Reeves. 1997. U.S. Pacific Marine Mammal Stock Assessments: 

1996. U.S. Dep. Commer. NOAA Tech. Memo. NMFS_SWFSC-248. 223 pp. 

Barlow, J., R. W. Baird, J. E. Heyning, K. Wynne, A. M. Manville, II, L. F. Lowry, D. Hanan, J. Sease, and 

V. N. Burkanov. 1994. A review of cetacean and pinniped mortality in coastal fisheries along the 

west coast of the U.S. and Canada and the east coast of the Russian Federation. Rep. Int. Whal. 

Commn, Special Issue 15:405-425. 

199
Barlow, J. and G. A. Cameron. 2003. Field experiments show that acoustic pingers reduce marine mammal 

bycatch in the California drift gillnet fishery. Marine Mammal Science 19(2):265-283. 

Barlow, J. 2003. Preliminary estimates of the abundance of cetaceans along the U.S. west coast: 

1991_2001. Southwest Fisheries Science Center Administrative Report LJ_03_03. Available 

from SWFSC, 8604 La Jolla Shores Dr., La Jolla CA 92037. 31p. 

Berdegué, J. 2002. Depredación de las especies pelágicas reservadas a la pesca deportiva y especies en 

peligro de extinción con uso indiscriminado de artes de pesca no selectivas (palangres, FAD's, 

trampas para peces y redes de agallar fijas y a la deriva) por la flota palangrera Mexicana. 

Fundación para la conservación de los picudos. A.C. Mazatlán, Sinaloa, 21 de septiembre. 

Best, P. B. 1993. Increase rates in severely depleted stocks of baleen whales. ICES J. Mar. Sci. 50:169-

186. 

Brueggeman, J. J., G. A. Green, K. C. Balcomb, C. E. Bowlby, R. A. Grotefendt, K. T. Briggs, M. L. 

Bonnell, R. G. Ford, D. H. Varoujean, D. Heinemann, and D. G. Chapman. 1990. OregonWashington Marine Mammal and Seabird Survey: Information synthesis and hypothesis 

formulation. U.S. Department of the Interior, OCS Study MMS 89-0030. 

Calambokidis, J., S. Osmek, and J. L. Laake. 1997. Aerial surveys for marine mammals in Washington 

and British Columbia inside waters. Final Contract Report to National Marine Mammal 

Laboratory, Seattle, WA. 

Carretta, J.V. and S.J. Chivers. 2004. Preliminary estimates of marine mammal mortality and biological 

sampling of cetaceans in California gillnet fisheries for 2003. Paper SC/56/SM1 presented to the 

IWC Scientific Committee, June 2004 (unpublished). [Available from Southwest Fisheries 

Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 

92037, USA]. 

Carretta, J.V., S.J. Chivers, and K. Danil. 2005a. Preliminary estimates of marine mammal bycatch, 

mortality, and biological sampling of cetaceans in California gillnet fisheries for 2004. 

Administrative Report LJ-05-10, available from Southwest Fisheries Science Center, 8604 La 

Jolla Shores Drive, La Jolla, California, 92037. 17 p. 

Carretta, J.V., T. Price, D. Petersen, and R. Read. 2005b. Estimates of marine mammal, sea turtle, and 

seabird mortality in the California drift gillnet fishery for swordfish and thresher shark, 1996-

2002. Marine Fisheries Review 66(2):21-30.Dohl, T. P., R. C. Guess, M. L. Duman, and R. C. 

Helm. 1983. Cetaceans of central and northern California, 1980-83: Status, abundance, and 

distribution. Final Report to the Minerals Management Service, Contract No. 14-12-0001-29090. 

284p. 

Donovan, G. P. 1991. A review of IWC stock boundaries. Rept. Int. Whal. Commn., Special Issue 13:39-

68. 

Dorsey, E. M., S. J. Stern, A. R. Hoelzel, and J. Jacobsen. 1990. Minke whale (Balaenoptera

acutorostrata) from the west coast of North America: individual recognition and small-scale site 

fidelity. Rept. Int. Whal. Commn., Special Issue 12:357-368. 

Forney, K. A., J. Barlow, and J. V. Carretta. 1995. The abundance of cetaceans in California waters. Part 

II: Aerial surveys in winter and spring of 1991 and 1992. Fish. Bull. 93:15-26. 

Forney, K.A. 2007. Preliminary estimates of cetacean abundance along the U.S. west coast and within 

four National Marine Sanctuaries during 2005. U.S. Department of Commerce NOAA Technical 

Memorandum, NOAA-TM-NMFS-SWFSC-406. 27p. 

Green, G. A., J. J. Brueggeman, R. A. Grotefendt, C. E. Bowlby, M. L. Bonnell, K. C. Balcomb, III. 1992. 

Cetacean distribution and abundance off Oregon and Washington, 1989-1990. Ch. 1 In: J. J. 

Brueggeman (ed.). Oregon and Washington Marine Mammal and Seabird Surveys. Minerals 

Management Service Contract Report 14-12-0001-30426. 

Hanan, D. A. 1986. California Department of Fish and Game coastal marine mammal study, annual report 

for the period July 1, 1983 - June 30, 1984. Admin. Rept. LJ-86-16. Southwest Fisheries Science 

Center, National Marine Fisheries Service, P.O. Box 271, La Jolla, CA. 55 pp. 

Hanan, D. A., D. B. Holts, and A. L. Coan, Jr. 1993. The California drift gill net fishery for sharks and 

swordfish, 1981-82 through 1990-91. Calif. Dept. Fish and Game Fish. Bull. No. 175. 95 pp. 

Heyning, J. E., and T. D. Lewis. 1990. Fisheries interactions involving baleen whales off southern 

California. Rep. Int. Whal. Commn. 40:427-431. 

Holts, D. and O. Sosa-Nishizaki. 1998. Swordfish, Xiphias gladius, fisheries of the eastern North Pacific 

Ocean. In: I. Barrett, O. Sosa-Nishizaki and N. Bartoo (eds.). Biology and fisheries of swordfish, 

200
Xiphias gladius. Papers from the International Symposium on Pacific Swordfish, Ensenada 

Mexico, 11-14 December 1994. U.S. Dep. Commer., NOAA Tech. Rep. NMFS 142, 276 p. 

Julian, F. and M. Beeson. 1998. Estimates for marine mammal, turtle, and seabird mortality for two 

California gillnet fisheries: 1990-95. Fish. Bull. 96:271-284. 

Leatherwood, S., R. R. Reeves, W. F. Perrin, and W. E. Evans. 1982. Whales, dolphins, and porpoises of 

the eastern North Pacific and adjacent Arctic waters: A guide to their identification. NOAA 

Technical Rept. NMFS Circular 444. 245pp. 

Pierce, D. J., M. Alexandersdottie, S. J. Jeffries, P. Erstad, W. Beattie, and A. Chapman. 1996. 

Interactions of marbled murrelets and marine mammals with the 1994 Puget Sound sockeye gill 

net fishery. Final Report, Wash. Dept. Fish and Wildlife, Olympia, WA. 21pp. 

Rice, D. W. 1974. Whales and whale research in the eastern North Pacific. pp. 170-195 In: W. E. 

Schevill (ed.). The Whale Problem: A Status Report. Harvard Press, Cambridge, MA. 

Sosa-Nishizaki, O., R. De la Rosa Pacheco, R. Castro Longoria, M. Grijalva Chon, and J. De la Rosa 

Velez. 1993. Estudio biologico pesquero del pez (Xiphias gladius) y otras especies de picudos 

(marlins y pez vela). Rep. Int. CICESE, CTECT9306. 

Tershy, B. R., D. Breese, and C. S. Strong. 1990. Abundance, seasonal distribution and population 

composition of balaenopterid whales in the Canal de Ballenas, Gulf of California, Mexico. Rept. 

Int. Whal. Commn., Special Issue 12:369-375. 

Von Saunder, A. and J. Barlow. 1999. A report of the Oregon, California and Washington Line-transect 

Experiment (ORCAWALE) conducted in west coast waters during summer/fall 1996. U.S. Dep. 

Commer. NOAA Tech. Memo. NMFS-SWFSC-264. 40 pp. 

Wade, P. R. and T. Gerrodette. 1993. Estimates of cetacean abundance and distribution in the eastern 

tropical Pacific. Rept. Int. Whal. Commn. 43:477-493. 

201
Revised 03/15/2005 

ROUGH-TOOTHED DOLPHIN (Steno bredanensis): 

Hawaiian Stock 

STOCK DEFINITION AND 

GEOGRAPHIC RANGE 

 Rough-toothed dolphins are 

found throughout the world in tropical 

and warm-temperate waters (Miyazaki 

and Perrin 1994). They are present 

around all the main Hawaiian islands 

(Shallenberger 1981; Tomich 1986) and 

have been observed at least as far 

northwest as French Frigate Shoals 

(Nitta and Henderson 1993). Recent 

sighting locations of rough-toothed 

dolphins during a 2002 shipboard survey 

of waters within the U.S. Exclusive 

Economic Zone (EEZ) of the Hawaiian 

Islands are shown in Figure 1. Eight 

strandings have been reported from 

Maui, Oahu, and the island of Hawaii 

(Nitta 1991; Maldini 2005). Nothing is 

known about stock structure for this 

species in the North Pacific. 

Photographic identification studies 

around the main Hawaiian islands have 

not demonstrated any inter-island 

movement of this species (R.W. Baird, 

pers. comm.). For the Marine Mammal 

Protection Act (MMPA) stock assessment reports, there is a single Pacific management stock including only animals 

found within the U.S. EEZ of the Hawaiian Islands. 

POPULATION SIZE

 A population estimate for this species has been made in the eastern tropical Pacific (Wade and Gerrodette 

1993), but it is not known whether these animals are part of the same population that occurs around the Hawaiian 

Islands. As part of the Marine Mammal Research Program of the Acoustic Thermometry of Ocean Climate (ATOC) 

study, a total of twelve aerial surveys were conducted within about 25 nmi of the main Hawaiian Islands in 1993, 

1995 and 1998. An abundance estimate of 123 (CV=0.63) rough-toothed dolphins was calculated from the 

combined survey data (Mobley et al. 2000). This study underestimated the total number of rough-toothed dolphins 

within the U.S. EEZ off Hawaii, because areas around the Northwestern Hawaiian Islands (NWHI) and beyond 25 

nautical miles from the main islands were not surveyed. Furthermore, the data on which this estimate was based are 

now over 5 years old. A 2002 shipboard line-transect survey of the entire Hawaiian Islands EEZ resulted in an 

abundance estimate of 19,904 (CV=0.52) rough-toothed dolphins (Barlow 2003). This is currently the best available 

abundance estimate for this stock. 

 

Minimum Population Estimate

 The log-normal 20th percentile of the 2002 abundance estimate for Hawaiian Islands EEZ waters is 13,184 

rough-toothed dolphins. 

Current Population Trend

 No data are available on current population trend. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No data are available on current or maximum net productivity rate. 

W180 W175 W170 W165 W160 W155 W150

N10

N15

N20

N25

N30

N35

Figure 1. Rough-toothed dolphin sighting locations during the 2002 

shipboard cetacean survey of U.S. EEZ waters surrounding the 

Hawaiian Islands (Barlow 2003; see Appendix 2 for details on timing 

and location of survey effort). Outer line represents approximate 

boundary of survey area and U.S. EEZ.

202
POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size 

(13,184) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.50 

(for a stock of unknown status with no known fishery mortality or serious injury; Wade and Angliss 1997), resulting 

in a PBR of 132 rough-toothed dolphins per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

Information on fishery-related mortality and serious injury of cetaceans in Hawaiian waters is limited, but 

the gear types used in Hawaiian fisheries are responsible for marine mammal mortality and serious injury in other 

fisheries throughout U.S. waters. Gillnets appear to capture marine mammals wherever they are used, and float lines 

from lobster traps and longlines can be expected to occasionally entangle whales (Perrin et al. 1994). 

 Interactions with cetaceans have been reported for all Hawaiian pelagic fisheries, and some of these 

interactions involved rough-toothed dolphins (Nitta and Henderson 1993). None were observed hooked or 

entangled in the Hawaii-based longline fishery between 1994 and 2002, with approximately 4-25% of all effort 

observed (Forney 2004). Rough-toothed dolphins are known to take bait and catch from Hawaiian sport and 

commercial fisheries operating near the main islands and in a portion of the northwestern islands (Shallenberger 

1981; Schlais 1984; Nitta and Henderson 1993), and they have been specifically reported to interact with the day 

handline fishery for tuna (palu-ahi) and the troll fishery for billfish and tuna (Schlais 1984; Nitta and Henderson 

1993). Interaction rates between dolphins and the NWHI bottomfish fishery have been estimated based on studies 

conducted in 1990-1993, indicating that an average of 2.67 dolphin interactions, most likely involving bottlenose 

and rough-toothed dolphins, occurred for every 1000 fish brought on board (Kobayashi and Kawamoto 1995). 

Fishermen claim interactions with dolphins who steal bait and catch are increasing. It is not known whether these 

interactions result in serious injury or mortality of dolphins. 

STATUS OF STOCK

 The status of rough-toothed dolphins in Hawaiian waters relative to OSP is unknown, and there are 

insufficient data to evaluate trends in abundance. No habitat issues are known to be of concern for this species. 

They are not listed as “threatened” or “endangered” under the Endangered Species Act (1973), nor as “depleted” 

under the MMPA. Although information on rough-toothed dolphins in Hawaiian waters is limited, this stock would 

not be considered strategic under the 1994 amendments to the MMPA given the absence of reported fisheries related 

mortality or serious injury. However, there is no systematic monitoring of gillnet fisheries that may take this 

species, and the potential effects of interactions with the bottomfish fishery in the NWHI are not known. 

Insufficient information is available to determine whether the total fishery mortality and serious injury for roughtoothed dolphins is insignificant and approaching zero mortality and serious injury rate. 

REFERENCES

Barlow, J. 2003. Cetacean abundance in Hawaiian waters during summer/fall 2002. Admin. Rep. LJ-03-13. 

Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La 

Jolla, CA 92037. 

Forney, K.A. 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994_2002. 

Admin. Rep. LJ-04-07. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92037. 17 pp. 

Kobayashi, D. R. and K. E. Kawamoto. 1995. Evaluation of shark, dolphin, and monk seal interactions with 

Northwestern Hawaiian Island bottomfishing activity: a comparison of two time periods and an estimate of 

economic impacts. Fisheries Research 23: 11-22. 

Maldini, D., L. Mazzuca, and S. Atkinson. 2005. Odontocete stranding patterns in the Main Hawaiian Islands 

(1937-2002): How do they compare with live animal surveys? Pacific Science 59(1):55-67. 

Miyazaki, N. and W. F. Perrin. 1994. Rough-toothed dolphin Steno bredanensis (Lesson, 1828). In: S. H. 

Ridgway and R. Harrison (eds.), Handbook of Marine Mammals, Vol.5: The First Book of Dolphins, pp. 1-

21. Academic Press, 416 pp. 

Mobley, J. R. , Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and 

abundance of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. 

Rep. LJ-00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 26 pp. 

203
Nitta, E. 1991. The marine mammal stranding network for Hawaii: an overview. In: J.E. Reynolds III, D.K. Odell 

(eds.), Marine Mammal Strandings in the United States, pp.56-62. NOAA Tech. Rep. NMFS 98, 157 pp. 

Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

Perrin, W.F., G. P. Donovan and J. Barlow. 1994. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Special Issue 

15, 629 pp. 

Schlais, J.F. 1984. Thieving dolphins: A growing problem in Hawaii's fisheries. Sea Front. 30(5):293-298. 

Shallenberger, E.W. 1981. The status of Hawaiian cetaceans. Final report to U.S. Marine Mammal Commission. 

MMC-77/23, 79pp. 

Tomich, P. Q. 1986. Mammals in Hawaii: A Synopsis and Notational Bibliography. Bishop Museum Press, Hawaii, 

375 pp. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

Wade, P. R. and T. Gerrodette. 1993. Estimates of cetacean abundance and distribution in the eastern tropical 

Pacific. Rep. Int. Whal. Commn. 43:477-493. 

204
Revised 03/15/2005

RISSO'S DOLPHIN (Grampus griseus): Hawaiian Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE 

Risso's dolphins are found in tropical to 

warm-temperate waters worldwide 

(Kruse et al. 1999). Although they have 

been considered rare in Hawaiian waters 

(Shallenberger (1981), six sightings 

were made during a 2002 survey of the 

U.S. Exclusive Economic Zone (EEZ) of 

the Hawaiian Islands (Figure 1). There 

are five stranding records from the main 

islands (Nitta 1991; Maldini 2005). For 

the Marine Mammal Protection Act 

(MMPA) stock assessment reports, 

Risso's dolphins within the Pacific U.S. 

EEZ are divided into two discrete, noncontiguous areas: 1) Hawaiian waters 

(this report), and 2) waters off 

California, Oregon and Washington. 

POPULATION SIZE

 Population estimates have been 

made off Japan (Miyashita 1993) and in 

the eastern tropical Pacific (Wade and 

Gerrodette 1993), but it is not known 

whether these animals are part of the 

same population that occurs around the 

Hawaiian Islands and in the central North Pacific. As part of the Marine Mammal Research Program of the 

Acoustic Thermometry of Ocean Climate (ATOC) study, a total of twelve aerial surveys were conducted within 

about 25 nmi of the main Hawaiian Islands in 1993, 1995 and 1998 (Mobley et al. 2000). Only one sighting of a 

single Risso’s dolphin was made, and no abundance estimate was calculated. A 2002 shipboard line-transect survey 

of the entire Hawaiian Islands EEZ resulted in an abundance estimate of 2,351 (CV=0.65) Risso’s dolphins (Barlow 

2003). This is currently the best available abundance estimate for this stock. 

Minimum Population Estimate

 The log-normal 20th percentile of the 2002 abundance estimate is 1,426 Risso’s dolphins. 

Current Population Trend

 No data are available on current population trend. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No data are available on current or maximum net productivity rate for Hawaiian animals. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size 

(1,426) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.50 

(for a stock of unknown status with no known fishery mortality or serious injury within the U.S. EEZ of the 

Hawaiian Islands; Wade and Angliss 1997), resulting in a PBR of 14 Risso’s dolphins per year. 

HUMAN CAUSED MORTALITY AND SERIOUS INJURY 

Fishery Information

 Information on fishery-related mortality and serious injury of cetaceans in Hawaiian waters is limited, but 

the gear types used in Hawaiian fisheries are responsible for marine mammal mortality and serious injury in other 

W180 W175 W170 W165 W160 W155 W150

N10

N15

N20

N25

N30

N35

Figure 1. Risso's dolphin sighting locations during the 2002 

shipboard cetacean survey of U.S. EEZ waters surrounding the 

Hawaiian Islands (Barlow 2003; see Appendix 2 for details on timing 

and location of survey effort). Outer line represents approximate 

boundary of survey area and U.S. EEZ.

205
fisheries throughout U.S. waters. Gillnets appear to capture marine mammals wherever they are used, and float lines 

from lobster traps and longlines can be expected to occasionally entangle whales (Perrin et al. 1994). 

 Interactions with cetaceans have been reported for all Hawaiian pelagic fisheries (Nitta and Henderson 

1993), and some of these interactions 

involved Risso’s dolphins. Between 

1994 and 2002, seven Risso’s dolphins 

were observed hooked or entangled in 

the Hawaii-based longline fishery 

outside of U.S. EEZ waters, with 

approximately 4-25% of all effort 

observed (Table 1; Figure 2; Forney 

2004). During the 905 observed trips 

with 11,014 sets, the average interaction 

rate of Risso’s dolphins was one animal 

per 129 fishing trips, or one animal per 

1,573 sets. All Risso’s dolphins caught 

were considered seriously injured 

(Forney 2004), based on an evaluation of 

the observer’s description of the 

interaction and following established 

guidelines for assessing serious injury in 

marine mammals (Angliss and Demaster 

1998). Average 5-yr estimates of annual 

mortality and serious injury for 1998-

2002 are 8.2 (CV = 0.66) Risso’s 

dolphins outside of U.S. EEZs, and none 

within the Hawaiian Islands EEZ. 

Several additional unidentified cetaceans, 

which may have been Risso’s dolphins, 

were also taken in this fishery (Figure 2, 

Forney 2004) in international waters and 

U.S. EEZ waters of Palmyra Island. In 

2001, regulations in the Hawaii-based 

longline fishery prohibited swordfish style fishing methods north of the equator in an effort to reduce sea turtle 

mortality (NMFS 2001); however, a portion of the Hawaii-based fleet subsequently moved to California and 

continued to fish in international waters of the North Pacific, in roughly the same areas as previously. No Risso’s 

dolphins were observed taken in the California-based longline fishery during 2001 and 2002, with roughly 5.5% 

observer coverage (Forney 2004). Preliminary data for 2003 indicate one Risso’s dolphin was hooked and released 

alive in international waters (NMFS/SWR, unpublished data). Since 2001, the Hawaii-based longline fishery has 

undergone further regulatory changes, but potential impacts of these changes on the rate of Risso’s dolphin takes are 

unknown. 

Table 1. Summary of available information on incidental mortality and serious injury of Risso’s dolphin (Hawaii 

stock) in commercial fisheries, within and outside of U.S. EEZs (Forney 2004). Mean annual takes are based on 

1998-2002 data unless otherwise indicated; n/a = not available. 

Mortality and Serious Injury 

outside of U.S. EEZ

Mortality and Serious Injury 

within Hawaiian Islands EEZ

Fishery Name Year Data Type

Percent 

Observer 

Coverage Observed Estimated 

(CV)

Mean Annual 

Takes 

(CV)

Observed Estimated 

(CV)

Mean Annual 

Takes 

(CV)

Hawaii-based 

longline fishery 

1998 

1999 

2000 

2001 

2002

observer 

data

4.6% 

3.5% 

11.8% 

22.7% 

24.9%

0 

1 

1 

1 

0

0 (-) 

29 (1.0) 

8 (1.0) 

4 (1.0) 

0 (-)

8.2 (0.66)

0 

0 

0 

0 

0

0 (-) 

0 (-) 

0 (-) 

0 (-) 

0 (-)

0 (-)

Figure 2. Locations of Risso's dolphin takes (filled diamonds) and 

possible takes of this species (open diamonds) in the Hawaii-based 

longline fishery, 1994-2002. Solid lines represent the U.S. EEZs.

Set locations in this fishery are summarized in Appendix 1.

206
Mortality and Serious Injury 

outside of U.S. EEZ

Mortality and Serious Injury 

within Hawaiian Islands EEZ

Fishery Name Year Data Type

Percent 

Observer 

Coverage Observed Estimated 

(CV)

Mean Annual 

Takes 

(CV)

Observed Estimated 

(CV)

Mean Annual 

Takes 

(CV)

California-based 

longline fishery

2001 

2002 

2003

observer 

data 

observer 

data

5.5% 

(2001-02) 

n/a

0 

0 

1

0 (-) 

0 (-) 

n/a

01

Minimum total annual takes within U.S. EEZ waters 0 (-)

1

Mean annual takes for the California-based longline fishery are based on 2001-2002. 

 Interaction rates between dolphins and the NWHI bottomfish fishery have been estimated based on studies 

conducted in 1990-1993, indicating that an average of 2.67 dolphin interactions, most likely involving bottlenose 

and rough-toothed dolphins, occurred for every 1000 fish brought on board (Kobayashi and Kawamoto 1995). 

Fishermen claim interactions with dolphins who steal bait and catch are increasing. It is not known whether these 

interactions result in serious injury or mortality of dolphins, nor whether Risso’s dolphins are involved. 

STATUS OF STOCK 

 The status of Risso's dolphins in Hawaiian waters relative to OSP is unknown, and there are insufficient 

data to evaluate trends in abundance. No habitat issues are known to be of concern for this species. They are not 

listed as “threatened” or “endangered” under the Endangered Species Act (1973), nor as “depleted” under the 

MMPA. The Hawaiian stock of Risso’s dolphin is not considered strategic under the 1994 amendments to the 

MMPA given the absence of reported fisheries related mortality within the U.S. EEZs. The potential effect of 

injuries sustained by Risso’s dolphins in U.S. pelagic longline fisheries in international waters is not known. 

Insufficient information is available to determine whether the total fishery mortality and serious injury for Risso’s 

dolphins is insignificant and approaching zero mortality and serious injury rate. 

REFERENCES

Angliss, R. P. and D. P. DeMaster. 1998. Differentiating Serious and Non_Serious Injury of Marine Mammals 

Taken Incidental to Commercial Fishing Operations: Report of the Serious Injury Workshop 1_2 April 

1997, Silver Spring, Maryland. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR-13. 48 pp. 

Barlow, J. 2003. Cetacean abundance in Hawaiian waters during summer/fall 2002. Admin. Rep. LJ-03-13. 

Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La 

Jolla, CA 92037. 

Forney, K.A. 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994_2002. 

Admin. Rep. LJ-04-07. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92037. 17 pp. 

Kruse, S. K., D. K. Caldwell, and M. C. Caldwell. 1999. Risso's dolphin Grampus griseus. Pages 183-212 In: S. H. 

Ridgway and R. Harrison (eds.), Handbook of Marine Mammals, Volume 6. Academic Press, San Diego. 

Kobayashi, D. R. and K. E. Kawamoto. 1995. Evaluation of shark, dolphin, and monk seal interactions with 

Northwestern Hawaiian Island bottomfishing activity: a comparison of two time periods and an estimate of 

economic impacts. Fisheries Research 23: 11-22. 

Maldini, D., L. Mazzuca, and S. Atkinson. 2005. Odontocete stranding patterns in the Main Hawaiian Islands 

(1937-2002): How do they compare with live animal surveys? Pacific Science 59(1):55-67. 

Miyashita, T. 1993. Abundance of dolphin stocks in the western North Pacific taken by the Japanese drive fishery. 

Rep. Int. Whal. Commn. 43:417-437. 

Mobley, J. R. , Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and 

abundance of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. 

Rep. LJ-00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 26 pp. 

Nitta, E. 1991. The marine mammal stranding network for Hawaii: an overview. In: J.E. Reynolds III, D.K. Odell 

(eds.), Marine Mammal Strandings in the United States, pp.56-62. NOAA Tech. Rep. NMFS 98, 157 pp. 

Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

207
NMFS, Southwest Region, Observer Program, 501 W. Ocean Blvd, Long Beach, CA, 90802. 

NMFS 2001. Western Pacific Pelagic Fisheries Biological Opinion. Available from Pacific Islands Region, 1602 

Kapiolani Blvd, Suite 1110, Honolulu, HI 96814 (http://swr.nmfs.noaa.gov/pir). 

Perrin, W.F., G. P. Donovan and J. Barlow. 1994. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Special Issue 

15, 629 pp. 

Shallenberger, E.W. 1981. The status of Hawaiian cetaceans. Final report to U.S. Marine Mammal Commission. 

MMC-77/23, 79pp. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

Wade, P. R. and T. Gerrodette. 1993. Estimates of cetacean abundance and distribution in the eastern tropical 

Pacific. Rep. Int. Whal. Commn. 43:477-493. 

208
Revised 12/15/2006

BOTTLENOSE DOLPHIN (Tursiops truncatus): Hawaiian Stock

STOCK DEFINITION AND GEOGRAPHIC RANGE 

Bottlenose dolphins are widely distributed 

throughout the world in tropical and warmtemperate waters. The species is primarily coastal 

in much of its range, but there are populations in 

some offshore deepwater areas as well. Separate 

offshore and coastal forms have been identified 

along continental coasts in several areas (Ross and 

Cockcroft 1990; Van Waerebeek et al. 1990), and 

there is some evidence that similar onshoreoffshore forms may exist in Hawaiian waters

(Martien et al 2005; Baird et al, in prep). 

 Bottlenose dolphins are common 

throughout the Hawaiian Islands, from the island of 

Hawaii to Kure Atoll (Shallenberger 1981). Twelve 

strandings have been reported within the main 

Hawaiian Islands (Nitta 1991, Maldini 2003). 

Recent sighting locations based on a 2002 

shipboard survey of waters within the U.S. 

Exclusive Economic Zone (EEZ) of the Hawaiian 

Islands are shown in Figure 1. In the Hawaiian 

Islands, they are found in shallow inshore waters 

and deep water (Baird et al. 2003). 

In their analysis of sightings of bottlenose 

dolphins in the eastern tropical Pacific (ETP), Scott and Chivers (1990) noted that there was a large hiatus between 

the westernmost sightings and the Hawaiian Islands. These data suggest that bottlenose dolphins in Hawaiian waters, 

belong to a separate stock from those in the ETP. Recent nearshore photo-identification studies off Oahu, Maui, 

Lanai, Kauai, Niihau, and Hawaii suggest limited movement of bottlenose dolphins between islands and into 

offshore waters (Baird et al. 2002; 2003). Further analyses of these data (Baird et al., in prep), along with recent 

genetic analyses (Martien et al. 2005) suggest that up to five different stocks of bottlenose dolphins may exist in 

Hawaiian EEZ waters: 1) the “4-Island Region” (Moloka‘i, Lana‘i, Maui, Kaho‘olawe) 2) Oahu, 3) Kauai, Niihau & 

Hawaii, 4) Offshore Kauai & Niihau and 5) Offshore Oahu. However, the limited number of bottlenose dolphin 

groups sampled in these studies preclude any strong inference regarding stock structure within the Hawaiian EEZ at 

this time. Estimates of abundance and potential biological removals will be presented separately for the 4-Island 

Region, which currently is the only region with detailed information. For the Marine Mammal Protection Act 

(MMPA) stock assessment reports, bottlenose dolphins within the Pacific U.S. EEZ are divided into three stocks: 1) 

Hawaiian Stock (this report), 2) California, Oregon and Washington offshore stock, and 3) California coastal stock. 

POPULATION SIZE

 Population estimates have been made in Japanese waters (Miyashita 1993) and the eastern tropical Pacific 

(Wade and Gerrodette 1993), but it is not known whether these animals are part of the same population that occurs 

around the Hawaiian Islands. Photographic mark-recapture studies off Maui and Lanai estimated 134 (95% C.I. 

107-180) bottlenose dolphins inhabiting that area (Baird et al. 2002). More recently, a minimum of 235 distinct 

bottlenose dolphins were identified around all the main Hawaiian Islands (Baird et al. 2006). As part of the Marine 

Mammal Research Program of the Acoustic Thermometry of Ocean Climate (ATOC) study, a total of twelve aerial 

surveys were conducted within about 25 nmi of the main Hawaiian Islands in 1993, 1995 and 1998. An abundance 

estimate of 743 (CV=0.56) bottlenose dolphins was calculated from the combined survey data (Mobley et al. 2000). 

This abundance underestimates the total number of bottlenose dolphins within the U.S. EEZ off Hawaii, because 

areas around the Northwestern Hawaiian Islands (NWHI) and beyond 25 nautical miles from the main islands were 

not surveyed. Furthermore, the data on which this estimate was based are now over 5 years old. A 2002 shipboard 

line-transect survey of the entire Hawaiian Islands EEZ resulted in an abundance estimate of 3,215 (CV= 0.59) 

bottlenose dolphins (Barlow 2006). This is currently the best available abundance estimate for the Hawaiian Islands 

EEZ stock. If the bottlenose dolphins in the 4-Island Region comprise a distinct stock, the most recent available 

Figure 1. Bottlenose dolphin sighting locations during the 

2002 shipboard cetacean survey of U.S. EEZ waters 

surrounding the Hawaiian Islands (Barlow 2006; see 

Appendix 2 for details on timing and location of survey 

effort). Outer line represents approximate boundary of 

survey area and U.S. EEZ. 

W180 W175 W170 W165 W160 W155 W150

N10

N15

N20

N25

N30

N35

209
estimate is the number of individuals identified during photo-identification studies between 1999 and 2003, 141 

dolphins (Baird et al., in prep). 

 

Minimum Population Estimate

 The log-normal 20th percentile of the 2002 abundance estimate is 2,029 bottlenose dolphins. The 

minimum population estimate for bottlenose dolphins in the Four-Island Region, based on photo-identification 

methods, is 68 dolphins (the number or of unique individuals identified between 1999 and 2003; Baird et al. 2003). 

 Current Population Trend

 No data are available on current population trend. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No data are available on current or maximum net productivity rate for this species in Hawaiian waters. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size 

(2,029) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.40 

(for a stock of unknown status with a Hawaiian Islands EEZ fishery mortality and serious injury rate CV > 0.80; 

Wade and Angliss 1997), resulting in a PBR of 16 bottlenose dolphins per year. If bottlenose dolphins in the 4-

Island Region comprise a separate stock, the PBR would be the minimum population estimate (141) times one half 

the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.50 (for a stock of 

unknown status with no reported fishery mortality during the last five years; Wade and Angliss 1997), resulting in a 

PBR of 1.4 bottlenose dolphins per year. 

HUMAN CAUSED MORTALITY AND SERIOUS INJURY 

Fishery Information

 Information on fishery-related mortality 

of cetaceans in Hawaiian waters is limited, but the 

gear types used in Hawaiian fisheries are 

responsible for marine mammal mortality and 

serious injury in other fisheries throughout U.S. 

waters. Gillnets appear to capture marine 

mammals wherever they are used, and float lines 

from lobster traps and longlines can be expected 

to occasionally entangle whales (Perrin et al. 

1994). In Hawaii, some mortality of bottlenose 

dolphins has been observed in inshore gillnets, but 

no estimate of annual human-caused mortality and 

serious injury is available, because these fisheries 

are not observed or monitored. 

 Interactions with cetaceans have been 

reported for all Hawaiian pelagic fisheries, and 

some of these interactions involved bottlenose 

dolphins (Nitta and Henderson 1993). Between 

1994 and 2002 three bottlenose dolphins were 

observed hooked or entangled in the Hawaii-based 

longline fishery, with approximately 4-26% of all 

effort observed (Table 1; Forney and Kobayashi 

2005). During 18,353 observed sets, the average 

interaction rate of bottlenose dolphins was 0.16 

animals per 1,000 sets. One of the bottlenose 

dolphins was killed, and the other two were 

considered seriously injured (Forney and Kobayashi 2005), based on an evaluation of the observer’s description of 

the interaction and following established guidelines for assessing serious injury in marine mammals (Angliss and 

Demaster 1998). Average 5-yr estimates of annual mortality and serious injury for 2000-2004 are 0.8 (CV = 1.00) 

bottlenose dolphins within the Hawaiian Islands EEZ, and none outside of U.S. EEZs. Six additional unidentified 

Figure 2. Locations of observed bottlenose dolphin takes 

(filled diamonds) and possible takes of this species (open 

diamonds) in the Hawaii-based longline fishery, 1994-2004. 

Solid lines represent the U. S. EEZ. Set locations in this 

fishery are summarized in Appendix 1. 

210
cetaceans, which may have been bottlenose dolphins, were also taken in this fishery (Figure 2, Forney and 

Kobayashi 2005). Since 2001, the Hawaii-based longline fishery has undergone a series of regulatory changes, 

primarily to protect sea turtles (NMFS 2001). Potential impacts of these regulatory changes on the rate of bottlenose 

dolphin takes are unknown. 

 Bottlenose dolphins are one of the species commonly reported to take bait and catch from several Hawaiian 

sport and commercial fisheries (Nitta and Henderson 1993; Schlais 1984). Observations of bottlenose dolphins 

taking bait or catch have also been made in the day handline fishery (palu-ahi) for tuna, the handline fishery for 

mackerel scad, the troll fishery for billfish and tuna, and the inshore set gillnet fishery (Nitta and Henderson 1993). 

Nitta and Henderson (1993) indicated that bottlenose dolphins remove bait and catch from handlines used to catch 

bottomfish off the island of Hawaii and Kaula Island and on several banks of the Northwestern Hawaiian Islands. 

Fishermen claim interactions with dolphins that steal bait and catch are increasing. Interaction rates between 

dolphins and the NWHI bottomfish fishery have been estimated based on studies conducted in 1990-1993, 

indicating that an average of 2.67 dolphin interactions, most likely involving bottlenose and rough-toothed dolphins, 

occurred for every 1000 fish brought on board (Kobayashi and Kawamoto 1995). It is not known whether these 

interactions result in serious injury or mortality of dolphins. Beginning in the early 1970s the National Marine 

Fisheries Service received reports of fishermen shooting at bottlenose dolphins to deter them from taking fish 

catches (Nitta and Henderson 1993). Nitta and Henderson (1993) also reported that one bottlenose dolphin calf was 

removed from small-mesh set gillnet off Maui in 1991 and expressed surprise that bottlenose dolphins are "rarely 

reported entangled or raiding set gill nets in Hawaii," considering that they so often remove fish from fishing lines. 

One bottlenose dolphin entangled in a gillnet was reported stranded on Maui in 1998 (NMFS/PIR, unpublished data; 

Maldini 2003). 

Table 1. Summary of available information on incidental mortality and serious injury of bottlenose dolphins 

(Hawaii stock) in commercial and gillnet fisheries, within and outside of the U.S. EEZs (Forney and Kobayashi 

2005; NMFS/PIR unpublished data). Mean annual takes are based on 2000-2004 data unless otherwise indicated; n/a 

= not available. 

Mortality and Serious Injury 

outside of U.S. EEZs 

Mortality and Serious Injury 

within Hawaiian Islands EEZ 

Fishery Name Year Data Type 

Percent 

Observer 

Coverage Observed Estimated 

(CV) 

Mean Annual 

Takes 

(CV) 

Observed Estimated 

(CV) 

Mean Annual 

Takes 

(CV) 

Hawaii-based 

longline fishery 

2000 

2001 

2002 

2003 

2004 

observer 

data 

11.0% 

23.0% 

24.8% 

21.9% 

25.7% 

0 

0 

0 

0 

0 

0 (-) 

0 (-) 

0 (-) 

0 (-) 

0 (-) 

0 (-) 

0 

0 

0 

1 

0 

0 (-) 

0 (-) 

0 (-) 

4 (1.0) 

0 (-) 

0.8 (1.0) 

Minimum total annual takes within U.S. EEZ waters 0.8 (1.0) 

STATUS OF STOCK 

 The status of bottlenose dolphins in Hawaiian waters relative to OSP is unknown, and there are insufficient 

data to evaluate trends in abundance. No habitat issues are known to be of concern for this species. They are not 

listed as “threatened” or “endangered” under the Endangered Species Act (1973), nor as “depleted” under the 

MMPA. The Hawaiian stock of bottlenose dolphins is not considered strategic under the 1994 amendments to the 

MMPA, because the estimated rate of fisheries related mortality or serious injury within the Hawaiian Islands EEZ 

(0.8 animals per year) is less than the PBR (16). However, there is no systematic monitoring of gillnet fisheries that 

may take this species, and the potential effects of interactions with the Hawaii-based longline fishery in international 

waters or the bottomfish fishery in the NWHI are not known. Insufficient information is available to determine 

whether the total fishery mortality and serious injury for bottlenose dolphins is insignificant and approaching zero 

mortality and serious injury rate. 

REFERENCES 

Angliss, R. P. and D. P. DeMaster. 1998. Differentiating Serious and Non-Serious Injury of Marine Mammals 

Taken Incidental to Commercial Fishing Operations: Report of the Serious Injury Workshop 1-2 April 

1997, Silver Spring, Maryland. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR-13. 48 pp.

Baird, R. W., A. M. Gorgone, and D. L. Webster. 2002. An examination of movements of bottlenose dolphins 

between islands in the Hawaiian Island Chain. Report prepared under contract # 40JGNF110270 to the 

Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La 

211
Jolla, CA 92037, USA. 10p. 

Baird, R.W., McSweeney D.J., Webster, D.L., Gorgone, A.M., and Ligon, A.D. 2003. Studies of odontocete 

population structure in Hawaiian waters: Results of a survey through the main Hawaiian Islands in May 

and June 2003. Report prepared under contract #AB133F-02-CN-0106 to the Southwest Fisheries Science 

Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 92037, USA. 25 pp. 

Baird, R.W., G.S. Schorr, D.L. Webster, S.D. Mahaffy, A.B. Douglas, A.M. Gorgone, and D.J. McSweeney. 2006. 

A survey for odontocete cetaceans off Kaua'i and Ni'ihau, Hawai'i, during October and November 2005: 

evidence for population structure and site fidelity. Report prepared under contract #AB133F05SE519 to 

Pacific Islands Fisheries Science Center, National Marine Fisheries Service, 2570 Dole Street, Honolulu, 

HI 96822, USA. 16p. 

Barlow, J. 2006. Cetacean abundance in Hawaiian waters estimated from a summer/fall survey in 2002. Marine 

Mammal Science 22: 446–464. 

Forney, K.A. 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994-2002. 

Admin. Rep. LJ-04-07. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92037.

Forney, K.A. and D. Kobayashi. 2005. Updated estimates of mortality and injury of cetaceans in the Hawaii-based 

longline fishery, 1994-2004. Draft report. Document PSRG-07 presented to the Pacific Scientific Review 

Group, November 16-17, 2005. Available from Southwest Fisheries Science Center, National Marine 

Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 92037. 

Kobayashi, D. R. and K. E. Kawamoto. 1995. Evaluation of shark, dolphin, and monk seal interactions with 

Northwestern Hawaiian Island bottomfishing activity: a comparison of two time periods and an estimate of 

economic impacts. Fisheries Research 23: 11-22. 

Maldini, D. 2003. Abundance and distribution patterns of Hawaiian odontocetes: focus on O’ahu. Doctoral 

dissertation, University of Hawai’i at Manoa. 122 pp.

Martien, K., R.W. Baird, and K. Robertson. 2005. Population structure of bottlenose dolphins around the main 

Hawaiian Islands. Document PSRG-08 presented to the Pacific Scientific Review Group, January 3-5, 

2005. Available from Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92037. 

Miyashita, T. 1993. Abundance of dolphin stocks in the western North Pacific taken by the Japanese drive fishery. 

Rep. Int. Whal. Commn. 43:417-437. 

Mobley, J. R. , Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and 

abundance of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. 

Rep. LJ-00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 26 pp. 

Nitta, E. 1991. The marine mammal stranding network for Hawaii: an overview. In: J.E. Reynolds III, D.K. Odell 

(eds.), Marine Mammal Strandings in the United States, pp.56-62. NOAA Tech. Rep. NMFS 98, 157 pp. 

Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

NMFS, Pacific Islands Region, Observer Program, 1602 Kapiolani Blvd, Suite 1110, Honolulu, HI 96814. 

NMFS 2001. Western Pacific Pelagic Fisheries Biological Opinion. Available from Pacific Islands Region, 1602 

Kapiolani Blvd, Suite 1110, Honolulu, HI 96814 (http://swr.nmfs.noaa.gov/pir). 

Perrin, W.F., G. P. Donovan and J. Barlow. 1994. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Special Issue 

15, 629 pp. 

Ross, G.J.B. and V. G. Cockcroft. 1990. Comments on Australian bottlenose dolphins and the taxonomic status of 

Tursiops aduncus (Ehrenberg, 1832). In: The Bottlenose Dolphin (eds. S. Leatherwood and R. Reeves). 

pp. 101-128. Academic Press, 653pp. 

Schlais, J.F. 1984. Thieving dolphins: A growing problem in Hawaii's fisheries. Sea Front. 30(5):293-298. 

Scott, M. D. and S. J. Chivers. 1990. Distribution and herd structure of bottlenose dolphins in the eastern tropical 

Pacific Ocean. In: The Bottlenose Dolphin (eds. S. Leatherwood and R. Reeves). pp. 387-402. Academic 

Press, 653pp. 

Shallenberger, E.W. 1981. The status of Hawaiian cetaceans. Final report to U.S. Marine Mammal Commission. 

MMC-77/23, 79pp. 

Van Waerebeek, K., J. C. Reyes, A. J. Read, and J. S. McKinnon. 1990. Preliminary observations of bottlenose 

dolphins from the Pacific coast of South America. In: The Bottlenose Dolphin (eds. S. Leatherwood and R. 

Reeves). pp. 143-154. Academic Press, 653 pp. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

212
Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

Wade, P. R. and T. Gerrodette. 1993. Estimates of cetacean abundance and distribution in the eastern tropical 

Pacific. Rep. Int. Whal. Commn. 43:477-493. 

213
Revised 03/15/2005

PANTROPICAL SPOTTED DOLPHIN 

(Stenella attenuata): Hawaiian Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE 

 Pantropical spotted dolphins are 

primarily found in tropical and 

subtropical waters worldwide (Perrin 

and Hohn 1994). Much of what is 

known about the species in the North 

Pacific has been learned from specimens 

obtained in the large directed fishery in 

Japan and in the eastern tropical Pacific 

(ETP) tuna purse-seine fishery (Perrin 

and Hohn 1994). These dolphins are 

common and abundant throughout the 

Hawaiian archipelago, particularly in 

channels between islands, over offshore 

banks (e.g. Penguin Banks), and off the 

lee shores of the islands (see 

Shallenberger 1981). Recent sighting 

locations from a 2002 shipboard survey 

of waters within the U.S. Exclusive 

Economic Zone (EEZ) of the Hawaiian 

Islands are shown in Figure 1 (Barlow 

2003). Twelve strandings of this species 

have been documented in Hawaii (Nitta 

1991, Maldini 2005). Morphological 

differences and distribution patterns 

have been used to establish that the 

spotted dolphins around Hawaii belong to a stock that is distinct from those in the ETP (Perrin 1975; Dizon et al. 

1994; Perrin et al. 1994b). Their possible affinities with other stocks elsewhere in the Pacific have not been 

investigated. 

 Fishery interactions with pantropical spotted dolphins demonstrate that this species also occurs in U.S. EEZ 

waters around Palmyra Island (Figure 2), but it is not known whether these animals are part of the Hawaiian stock or 

a separate stock of pantropical spotted dolphins. Based on patterns of movement and population structure observed 

in other island-associated cetaceans (Norris and Dohl 1980; Norris et al.1994; Baird et al. 2001, 2003; S. Chivers, 

pers. comm.), the animals around Palmyra Island may represent a separate stock. Efforts are currently underway to 

obtain additional tissue samples of pantropical spotted dolphins for further studies of population structure in the 

North Pacific Ocean. There are at least 113 genetic samples available from Hawaiian waters for stock structure 

analyses (R.W. Baird, pers. comm.). For the Marine Mammal Protection Act (MMPA) stock assessment reports, 

there is a single Pacific management stock including only animals found within the U.S. EEZ of the Hawaiian 

Islands. Spotted dolphins involved in eastern tropical Pacific tuna purse-seine fisheries are managed separately 

under the MMPA. Information on pantropical spotted dolphins around Palmyra Island will provisionally be 

included with this stock assessment report, recognizing that separate stock status may be warranted for these animals 

in the future. Estimates of abundance, potential biological removals, and status determinations will be presented 

separately for U.S. EEZ waters of the Hawaiian Islands and Palmyra Island. 

 

POPULATION SIZE

 Population estimates are available for Japanese waters (Miyashita 1993) and the eastern tropical Pacific 

(Wade and Gerrodette 1993). As part of the Marine Mammal Research Program of the Acoustic Thermometry of 

Ocean Climate (ATOC) study, a total of twelve aerial surveys were conducted within about 25 nmi of the main 

Hawaiian Islands in 1993, 1995 and 1998. An abundance estimate of 2,928 (CV=0.45) pantropical spotted dolphins 

was calculated from the combined survey data (Mobley et al. 2000). This abundance underestimates the total 

number of pantropical spotted dolphins within the U.S. EEZ off Hawaii, because areas around the Northwestern 

W180 W175 W170 W165 W160 W155 W150

N10

N15

N20

N25

N30

N35

Figure 1. Pantropical spotted dolphin sighting locations during the 

2002 shipboard survey of U.S. EEZ waters surrounding the Hawaiian 

Islands (Barlow 2003; see Appendix 2 for details on timing and 

location of survey effort). Outer line represents approximate 

boundary of survey area and U.S. EEZ. 

214
Hawaiian Islands (NWHI) and beyond 25 nautical miles from the main islands were not surveyed. Furthermore, the 

data on which this estimate was based are now over 5 years old. A 2002 shipboard line-transect survey of the entire 

Hawaiian Islands EEZ resulted in an abundance estimate of 10,260 (CV=0.41) pantropical spotted dolphins (Barlow 

2003). This is currently the best available abundance estimate for pantropical spotted dolphins within the Hawaiian 

Islands EEZ. 

 No abundance estimates are currently available for pantropical spotted dolphins in U.S. EEZ waters of 

Palmyra Island; however, density estimates for pantropical spotted dolphins in other Pacific regions can provide a 

range of likely abundance estimates in this unsurveyed region. Published estimates of pantropical spotted dolphins 

(animals per km2) in the Pacific are: 0.0046 (CV=0.41) for the U.S. EEZ of the Hawaiian Islands (Barlow 2003); 

0.0407 (CV=0.45) for nearshore waters surrounding the main Hawaiian Islands (Mobley et al. 2000), 0.0678 

(CV=0.15) and 0.1064 (CV=0.09) for the eastern tropical Pacific Ocean (Wade and Gerrodette 1993; Ferguson and 

Barlow 2003), and 0.0731 (CV=0.33) for the eastern tropical Pacific Ocean west of 120°W and north of 5°N 

(Ferguson and Barlow 2003). Applying the lowest and highest of these density estimates to U.S. EEZ waters 

surrounding Palmyra Island (area size = 347,216 km2) yields a range of plausible abundance estimates of 1,590 - 

36,928 pantropical spotted dolphins. 

Minimum Population Estimate

 The log-normal 20th percentile of the 2002 abundance estimate for the Hawaiian Islands EEZ (Barlow 

2003) is 7,362 pantropical spotted dolphins. No minimum population estimate is currently available for waters 

surrounding Palmyra Island, but the pantropical spotted dolphin density estimates from other Pacific regions 

(Barlow 2003, Mobley et al. 2000, Wade and Gerrodette 1993, Ferguson and Barlow 2003; see above) can provide a 

range of likely values. The lognormal 20th percentiles of plausible abundance estimates for the Palmyra Island 

EEZ, based on the densities observed elsewhere, range from 1,141 - 34,238 pantropical spotted dolphins. 

Current Population Trend

 No data are available on current population trend. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No data are available on current or maximum net productivity rate. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for the Hawaiian pantropical spotted dolphin stock is 

calculated as the minimum population size (7,362) times one half the default maximum net growth rate for cetaceans 

(1⁄2 of 4%) times a recovery factor of 0.50 (for a species of unknown status with no known fishery mortality within 

the U.S. EEZ of the Hawaiian Islands; Wade and Angliss 1997), resulting in a PBR of 74 pantropical spotted 

dolphins per year. No separate PBR can presently be calculated for pantropical spotted dolphins within the Palmyra 

Island EEZ, but based on the range of plausible minimum abundance estimates (1,141 - 34,238), a recovery factor of 

0.40 (for a species of unknown status with a fishery mortality and serious injury rate CV > 0.80 within the Palmyra 

Islands EEZ; Wade and Angliss 1997), and the default growth rate (1⁄2 of 4%), the PBR would likely fall between 9.1 

and 274 pantropical spotted dolphins per year. 

 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information 

Information on fishery-related mortality of cetaceans in Hawaiian waters is limited, but the gear types used in 

Hawaiian fisheries are responsible for marine mammal mortality and serious injury in other fisheries throughout 

U.S. waters. Gillnets appear to capture marine mammals wherever they are used, and float lines from lobster traps 

and longlines can be expected to occasionally entangle whales (Perrin et al. 1994a). Interactions with cetaceans have 

been reported for all Hawaiian pelagic fisheries (Nitta and Henderson 1993). Between 1994 and 2002 one 

pantropical spotted dolphin was observed entangled and killed in the Hawaii-based longline fishery within U.S. EEZ 

waters, with approximately 4-25% of all effort observed (Table 1; Forney 2004). During the 905 observed trips with 

11,014 sets, the average take rate of pantropical spotted dolphins was one animal per 905 fishing trips, or one 

animal per 11,014 sets. Average 5-yr estimates of annual mortality and serious injury for pantropical spotted 

dolphins during 1998-2002 are zero outside of the U.S. EEZs, and 0.8 (CV=1.0) within the U.S. EEZ of Palmyra 

Island. No pantropical spotted dolphins were observed taken within the Hawaiian Islands EEZ during 1998-2002. 

One unidentified cetacean, which may have been a pantropical spotted dolphin, was also taken in this fishery within 

the EEZ of Palmyra Island (Figure 2, Forney 2004). Since 2001, the Hawaii-based longline fishery has undergone a 

215
series of regulatory changes, primarily to 

protect sea turtles (NMFS 2001). 

Potential impacts of these regulatory 

changes on the rate of pantropical spotted 

dolphin takes are unknown. Interaction 

rates between dolphins and the NWHI 

bottomfish fishery have been estimated 

based on studies conducted in 1990-1993, 

indicating that an average of 2.67 dolphin 

interactions, most likely involving 

bottlenose and rough-toothed dolphins, 

occurred for every 1000 fish brought on 

board (Kobayashi and Kawamoto 1995). 

Fishermen claim interactions with 

dolphins who steal bait and catch are 

increasing. It is not known whether these 

interactions result in serious injury or 

mortality of dolphins, nor whether 

pantropical spotted dolphins are involved. 

STATUS OF STOCK

 The status of pantropical spotted 

dolphins in Hawaiian waters relative to 

OSP is unknown, and there are 

insufficient data to evaluate trends in 

abundance. No habitat issues are known to 

be of concern for this species. They are 

not listed as “threatened” or “endangered” 

under the Endangered Species Act (1973), 

nor as “depleted” under the MMPA. The 

Hawaiian stock of pantropical spotted dolphins is not considered strategic under the 1994 amendments to the 

MMPA, because the estimated rate of fisheries related mortality or serious injury within the Palmyra Island EEZ 

(0.8 animals per year) is less than the range of likely PBRs (9.1 – 274) for this region. Insufficient information is 

available to determine whether the total fishery mortality and serious injury for pantropical spotted dolphins is 

insignificant and approaching zero mortality and serious injury rate. 

Table 1. Summary of available information on incidental mortality and serious injury of pantropical spotted 

dolphins (Hawaiian stock) in commercial fisheries, within and outside of the U.S. EEZs (Forney 2004). Mean 

annual takes are based on 1998-2002 data unless otherwise indicated. 

Observed and estimated mortality and serious injury of pantropical spotted dolphins, by EEZ 

region

Outside of U.S. EEZs Hawaiian Islands EEZ Palmyra Island EEZ Fishery 

Name Year Data Type

Percent 

Observer 

Coverage

Obs.

Estimated 

(CV)

Mean 

Annual 

Takes 

(CV)

Obs.

Estimated 

(CV)

Mean 

Annual 

Takes 

(CV)

Obs. Estimated 

(CV)

Mean 

Annual 

Takes 

(CV)

Hawaiibased 

longline 

fishery 

1998 

1999 

2000 

2001 

2002

observer 

data

4.6% 

3.5% 

11.8% 

22.7% 

24.9%

0 

0 

0 

0 

0

0 

0 

0 

0 

0

0 (-) 

0 (-) 

0 (-) 

0 (-) 

0 (-)

0 

0 

0 

0 

0

0 (-) 

0 (-) 

0 (-) 

0 (-) 

0 (-)

0 (-)

0 

0 

0 

1 

0

0 (-) 

0 (-) 

0 (-) 

4 (1.0) 

0 (-)

0.8 (1.0)

Minimum total annual takes within U.S. EEZ waters 0.8 (1.0)

Figure 2. Locations of observed pantropical spotted dolphin take 

(filled diamond) and a possible take (open diamond) in the Hawaiian 

longline fishery, 1994-2002. Solid lines represent the U.S. EEZ. Set 

locations in this fishery are summarized in Appendix 1. 

216
REFERENCES

Baird, R. W., Ligon, A. D., Hooker, S. K., and A. M. Gorgone. 2001. Subsurface and nighttime behaviour of 

pantropical spotted dolphins in Hawai’i. Can. J. Zool. 79:988-996. 

Baird, R.W., McSweeney D.J., Webster, D.L., Gorgone, A.M., and Ligon, A.D. 2003. Studies of odontocete 

population structure in Hawaiian waters: Results of a survey through the main Hawaiian Islands in May 

and June 2003. Report prepared under contract #AB133F-02-CN-0106 to the Southwest Fisheries Science 

Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 92037, USA. 25 pp. 

Barlow, J. 2003. Cetacean abundance in Hawaiian waters during summer/fall 2002. Admin. Rep. LJ-03-13. 

Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La 

Jolla, CA 92037. 

Chivers, S. NMFS, Southwest Fisheries Science Center, 8604 La Jolla Shores Drive, La Jolla, CA 92037. 

Dizon, A. E., W. F. Perrin, and P. A. Akin. 1994. Stocks of dolphins (Stenella spp. and Delphinus delphis) in the 

eastern tropical Pacific: a phylogeographic classification. NOAA Tech. Rep. NMFS 119, 20 pp. 

Ferguson, M. C. and J. Barlow. 2003. Addendum: Spatial distribution and density of cetaceans in the eastern 

tropical Pacific Ocean based on summer/fall research vessel surveys in 1986-96. Administrative Report LJ01-04 (addendum), Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla 

Shores Drive, La Jolla, CA 92037. 

Forney, K.A. 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994_2002. 

Admin. Rep. LJ-04-07. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92037. 17 pp. 

Kobayashi, D. R. and K. E. Kawamoto. 1995. Evaluation of shark, dolphin, and monk seal interactions with 

Northwestern Hawaiian Island bottomfishing activity: a comparison of two time periods and an estimate of 

economic impacts. Fisheries Research 23: 11-22. 

Maldini, D., L. Mazzuca, and S. Atkinson. 2005. Odontocete stranding patterns in the Main Hawaiian Islands 

(1937-2002): How do they compare with live animal surveys? Pacific Science 59(1):55-67. 

Miyashita, T. 1993. Abundance of dolphin stocks in the western North Pacific taken by the Japanese drive fishery. 

Rep. Int. Whal. Commn. 43:417-437. 

Mobley, J. R. , Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and 

abundance of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. 

Rep. LJ-00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 26 pp. 

Nitta, E. 1991. The marine mammal stranding network for Hawaii: an overview. In: J.E. Reynolds III, D.K. Odell 

(eds.), Marine Mammal Strandings in the United States, pp.56-62. NOAA Tech. Rep. NMFS 98, 157 pp. 

Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

NMFS 2001. Western Pacific Pelagic Fisheries Biological Opinion. Available from Pacific Islands Region, 1602 

Kapiolani Blvd, Suite 1110, Honolulu, HI 96814 (http://swr.nmfs.noaa.gov/pir). 

Norris, K. S., B. Würsig, R. S. Wells, and M. Würsig. 1994. The Hawaiian Spinner Dolphin. University of 

California Press, 408 pp. 

Norris, K. S. and T. P. Dohl. 1980. Behavior of the Hawaiian spinner dolphin, Stenella longirostris. Fish. Bull.

77:821-849. 

Perrin, W. F. 1975. Variation of spotted and spinner porpoise (genus Stenella) in the eastern tropical Pacific and 

Hawaii. Bull. Scripps Inst. Oceanogr. 21, 206 pp. 

Perrin, W. F. and A. A. Hohn. 1994. Pantropical spotted dolphin Stenella attenuata. In: S. H. Ridgway and R. 

Harrison (eds.), Handbook of Marine Mammals, Vol.5: The First Book of Dolphins, pp 71-98. Academic 

Press, 416 pp. 

Perrin, W.F., G. P. Donovan and J. Barlow. 1994a. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Special Issue 

15, 629 pp. 

Perrin, W. F., G. D. Schnell, D. J. Hough, J. W. Gilpatrick, Jr., and J. V. Kashiwada. 1994b. Re-examination of 

geographical variation in cranial morphology of the pantropical spotted dolphin, Stenella attenuata, in the 

eastern Pacific. Fish. Bull. 92:324-346. 

Shallenberger, E.W. 1981. The status of Hawaiian cetaceans. Final report to U.S. Marine Mammal Commission. 

MMC-77/23, 79pp. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

217
Wade, P. R. and T. Gerrodette. 1993. Estimates of cetacean abundance and distribution in the eastern tropical 

Pacific. Rep. Int. Whal. Commn. 43:477-493. 

218
Revised 03/15/2005

SPINNER DOLPHIN (Stenella longirostris): Hawaiian Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

 Spinner dolphins are found 

throughout the world in tropical and 

warm-temperate waters (Perrin and 

Gilpatrick 1994). They are common and 

abundant throughout the entire Hawaiian 

archipelago (Shallenberger 1981; Norris 

and Dohl 1980; Norris et al. 1994), and 

26 strandings have been reported 

(Maldini 2005). Recent sighting 

locations from a 2002 shipboard survey 

of waters within the U.S. Exclusive 

Economic Zone (EEZ) of the main 

Hawaiian Islands (Barlow 2003) are 

shown in Figure 1. There is some 

suggestion from an intensive study of 

spinner dolphins off the Kona Coast of 

Hawaii that the waters surrounding this 

island may have a large, relatively stable 

"resident" population (Norris et al. 

1994). Currently, it is not known 

whether spinner dolphins regularly move 

between islands or island groups, or 

whether separate populations may exist. 

 Hawaiian spinner dolphins 

belong to a stock that is separate from those involved in the tuna purse-seine fishery in the eastern tropical Pacific 

(Perrin 1975; Dizon et al. 1994). The Hawaiian form is referable to the subspecies S. longirostris longirostris, 

which occurs pantropically (Perrin 1990). For the Marine Mammal Protection Act (MMPA) stock assessment 

reports, there is a single Pacific management stock including only animals found within the U.S. EEZ of the 

Hawaiian Islands. Spinner dolphins involved in eastern tropical Pacific tuna purse-seine fisheries are managed 

separately under the MMPA. 

POPULATION SIZE

 Although spinner dolphins are clearly among the most abundant cetaceans in Hawaiian waters, previously 

available population estimates apply only to the west coast of Hawaii. Norris et al. (1994) photo-identified 192 

individuals along the west coast of Hawaii and estimated 960 animals for this area in 1979-1980. Östman (1994) 

photoidentified 677 individual spinner dolphins in the same area from 1989 to 1992. Using the same estimation 

procedures as Norris et al. (1994), Östman (1994) estimated a population size of 2,334 for his study area along the 

Kona coast of Hawaii. As part of the Marine Mammal Research Program of the Acoustic Thermometry of Ocean 

Climate (ATOC) study, a total of twelve aerial surveys were conducted within about 25 nmi of the main Hawaiian 

Islands in 1993, 1995 and 1998. An abundance estimate of 3,184 (CV=0.37) spinner dolphins was calculated from 

the combined survey data (Mobley et al. 2000). This study underestimated the total number of spinner dolphins 

within the U.S. EEZ off Hawaii, because areas around the Northwestern Hawaiian Islands (NWHI) and beyond 25 

nautical miles from the main islands were not surveyed. Furthermore, the data on which this estimate was based are 

now over 5 years old. A 2002 shipboard line-transect survey of the entire Hawaiian Islands EEZ resulted in an 

abundance estimate of 2,805 (CV=0.66) spinner dolphins (Barlow 2003). This is currently the best available 

abundance estimate for this stock, but it may be negatively biased because relatively little survey effort occurred in 

nearshore areas where these dolphins are abundant. Nearshore aerial surveys are currently being conducted for this 

species. 

Minimum Population Estimate

 The log-normal 20th percentile of the 2002 abundance estimate is 1,690 spinner dolphins. 

W180 W175 W170 W165 W160 W155 W150

N10

N15

N20

N25

N30

N35

Figure 1. Spinner dolphin sighting locations during the 2002 

shipboard cetacean survey of U.S. EEZ waters surrounding the 

Hawaiian Islands (Barlow 2003; see Appendix 2 for details on timing 

and location of survey effort). Outer line indicates approximate 

boundary of survey area and U.S. EEZ.

219
Current Population Trend

 No data on current population trend are available. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES 

No information on current or maximum net productivity rate is currently available for the Hawaiian stock. 

 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size 

(1,690) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.50 

(for a species of unknown status with no estimated fishery mortality or serious injury within the U.S. EEZ of the 

Hawaiian Islands; Wade and Angliss 1997), resulting in a PBR of 17 spinner dolphins per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

 Information on fishery-related 

mortality of cetaceans in Hawaiian 

waters is limited, but the gear types used 

in Hawaiian fisheries are responsible for 

marine mammal mortality and serious 

injury in other fisheries throughout U.S. 

waters. Gillnets appear to capture marine 

mammals wherever they are used, and 

float lines from lobster traps and 

longlines can be expected to occasionally 

entangle whales (Perrin et al. 1994). In 

Hawaii, some entanglements of spinner 

dolphins have been observed (Nitta and 

Henderson 1993; NMFS/PIR, 

unpublished data), but no estimate of 

annual human-caused mortality and 

serious injury is available, because the 

nearshore gillnet fisheries are not 

observed or monitored. 

 Interactions with cetaceans have 

been reported for all Hawaiian pelagic 

fisheries (Nitta and Henderson 1993). 

Between 1994 and 2002, two spinner 

dolphins were observed hooked or 

entangled in the Hawaii-based longline 

fishery, with approximately 4-25% of all 

effort observed (Forney 2004). During 

the 905 observed trips with 11,014 sets, 

the average interaction rate of spinner 

dolphins was one animal per 453 fishing 

trips, or one animal per 5,507 sets. Neither of the animals caught was considered seriously injured (Forney 2004), 

based on an evaluation of the observer’s description of the interaction and following established guidelines for 

assessing serious injury in marine mammals (Angliss and Demaster 1998). The average 5-yr estimate of annual 

mortality and serious injury within the Hawaiian Islands EEZ during 1998-2002 is zero spinner dolphins. One 

additional unidentified cetacean, which may have been a spinner dolphin, was taken in this fishery within the U.S. 

EEZ surrounding Palmyra Island (Figure 2, Forney 2004). Since 2001, the Hawaii-based longline fishery has 

undergone a series of regulatory changes, primarily to protect sea turtles (NMFS 2001). Potential impacts of these 

regulatory changes on the rate of spinner dolphin takes are unknown. 

 Interaction rates between dolphins and the NWHI bottomfish fishery have been estimated based on studies 

conducted in 1990-1993, indicating that an average of 2.67 dolphin interactions, most likely involving bottlenose 

and rough-toothed dolphins, occurred for every 1000 fish brought on board (Kobayashi and Kawamoto 1995). 

Figure 2. Locations of observed spinner dolphin takes (filled 

diamonds) and possible takes of this species (open diamond) in the 

Hawaii-based longline fishery, 1994-2002. Solid lines represent the 

U.S. EEZ. Set locations in this fishery are summarized in Appendix 

1. 

220
Fishermen claim interactions with dolphins who steal bait and catch are increasing. It is not known whether these 

interactions result in serious injury or mortality of dolphins, nor whether spinner dolphins are involved. 

STATUS OF STOCK 

The status of spinner dolphins in Hawaiian waters relative to OSP is unknown, and there are insufficient 

data to evaluate trends in abundance. A habitat issue of increasing concern is the potential effect of swim-withdolphin programs and other tourism activities on spinner dolphins around the main Hawaiian Islands. Spinner 

dolphins are not listed as “threatened” or “endangered” under the Endangered Species Act (1973), nor as “depleted” 

under the MMPA. The Hawaiian stock of spinner dolphins is not considered a strategic stock under the 1994 

amendments to the MMPA, because the estimated rate of mortality and serious injury within the Hawaiian Islands 

EEZ is zero. However, there is no systematic monitoring of gillnet fisheries that may take this species. Insufficient 

information is available to determine whether the total fishery mortality and serious injury for spinner dolphins is 

insignificant and approaching zero mortality and serious injury rate.

REFERENCES 

Angliss, R. P. and D. P. DeMaster. 1998. Differentiating Serious and Non_Serious Injury of Marine Mammals 

Taken Incidental to Commercial Fishing Operations: Report of the Serious Injury Workshop 1_2 April 

1997, Silver Spring, Maryland. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR-13. 48 pp. 

Barlow, J. 2003. Cetacean abundance in Hawaiian waters during summer/fall 2002. Admin. Rep. LJ-03-13. 

Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La 

Jolla, CA 92038. 

Dizon, A. E., W. F. Perrin, and P. A. Akin. 1994. Stocks of dolphins (Stenella spp. and Delphinus delphis) in the 

eastern tropical Pacific: a phylogeographic classification. NOAA Tech. Rep. NMFS 119, 20 pp. 

Forney, K.A. 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994_2002. 

Admin. Rep. LJ-04-07. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92037. 17 pp. 

Kobayashi, D. R. and K. E. Kawamoto. 1995. Evaluation of shark, dolphin, and monk seal interactions with 

Northwestern Hawaiian Island bottomfishing activity: a comparison of two time periods and an estimate of 

economic impacts. Fisheries Research 23: 11-22. 

Maldini, D., L. Mazzuca, and S. Atkinson. 2005. Odontocete stranding patterns in the Main Hawaiian Islands 

(1937-2002): How do they compare with live animal surveys? Pacific Science 59(1):55-67. 

Mobley, J. R. , Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and 

abundance of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. 

Rep. LJ-00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 26 pp. 

Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

Norris, K. S., B. Würsig, R. S. Wells, and M. Würsig. 1994. The Hawaiian Spinner Dolphin. University of 

California Press, 408 pp. 

Norris, K. S. and T. P. Dohl. 1980. Behavior of the Hawaiian spinner dolphin, Stenella longirostris. Fish. Bull.

77:821-849. 

NMFS, Pacific Islands Region, Observer Program, 1602 Kapiolani Blvd, Suite 1110, Honolulu, HI 96814. 

NMFS 2001. Western Pacific Pelagic Fisheries Biological Opinion. Available from Pacific Islands Region, 1602 

Kapiolani Blvd, Suite 1110, Honolulu, HI 96814 (http://swr.nmfs.noaa.gov/pir). 

Östman, J. S. O. 1994. Social organization and social behavior of Hawaiian spinner dolphins (Stenella 

longirostris). Ph.D. dissertation, University of California, Santa Cruz, 114 pp. 

Perrin, W. F. 1975. Variation of spotted and spinner porpoise (genus Stenella) in the eastern tropical Pacific and 

Hawaii. Bull. Scripps Inst. Oceanogr. 21, 206 pp. 

Perrin, W. F. 1990. Subspecies of Stenella longirostris (Mammalia: Cetacea: Delphinidae). Proc. Biol. Soc. Wash. 

103:453-463. 

Perrin, W. F. and J. W. Gilpatrick, Jr. 1994. Spinner dolphin Stenella longirostris (Gray, 1828). In: S. H. Ridgway 

and R. Harrison (eds.), Handbook of Marine Mammals, Vol.5: The First Book of Dolphins, pp. 99-128. 

Academic Press, 416 pp. 

Perrin, W.F., G. P. Donovan and J. Barlow. 1994. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Special Issue 

15, 629 pp. 

221
Shallenberger, E.W. 1981. The status of Hawaiian cetaceans. Final report to U.S. Marine Mammal Commission. 

MMC-77/23, 79pp. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

222
Revised 03/15//2005

STRIPED DOLPHIN (Stenella coeruleoalba): Hawaiian Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

 Striped dolphins are found in 

tropical to warm-temperate waters 

throughout the world (Perrin et al. 

1994b). They have been documented in 

the Hawaiian Islands from 20 strandings 

(Nitta 1991, Maldini 2005), although 

sightings have historically been 

infrequent (Shallenberger 1981, Mobley 

et al. 2000). A comprehensive shipboard 

survey of the Hawaiian Exclusive 

Economic Zone (EEZ), resulted in 15 

sightings of striped dolphins (Figure 1; 

Barlow 2003). 

 Striped dolphins have been 

intensively exploited in the western 

North Pacific, where three migratory 

stocks are provisionally recognized 

(Kishiro and Kasuya 1993). In the 

eastern Pacific all striped dolphins are 

provisionally considered to belong to a 

single stock (Dizon et al. 1994). For the 

Marine Mammal Protection Act 

(MMPA) stock assessment reports, 

striped dolphins within the Pacific U.S. 

EEZ are divided into two discrete, noncontiguous areas: 1) waters off California, Oregon and Washington, and 2) waters around Hawaii (this report). 

Striped dolphins involved in eastern tropical Pacific tuna purse-seine fisheries are managed separately under the 

MMPA. 

POPULATION SIZE

 Population estimates are available for Japanese waters (Miyashita 1993) and the eastern tropical Pacific 

(Wade and Gerrodette 1993), but it is not known whether any of these animals are part of the same population that 

occurs around the Hawaiian Islands. As part of the Marine Mammal Research Program of the Acoustic 

Thermometry of Ocean Climate (ATOC) study, a total of twelve aerial surveys were conducted within about 25 nmi 

of the main Hawaiian Islands in 1993, 1995 and 1998. An abundance estimate of 114 (CV=1.19) striped dolphins 

was calculated from the combined survey data (Mobley et al. 2000). This study underestimated the total number of 

striped dolphins within the U.S. EEZ off Hawaii, because areas around the Northwestern Hawaiian Islands (NWHI) 

and beyond 25 nautical miles from the main islands were not surveyed. Furthermore, the data on which this estimate 

was based are now over 5 years old. A 2002 shipboard line-transect survey of the entire Hawaiian Islands EEZ 

resulted in an abundance estimate of 10,385 (CV=0.48) striped dolphins (Barlow 2003). This is currently the best 

available abundance estimate for this stock. 

Minimum Population Estimate

 The log-normal 20th percentile of the 2002 abundance estimate is 7,078 striped dolphins. 

Current Population Trend 

 No data are available on current population trend. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No data are available on current or maximum net productivity rate. 

W180 W175 W170 W165 W160 W155 W150

N10

N15

N20

N25

N30

N35

Figure 1. Striped dolphin sighting locations during the 2002 

shipboard survey of U.S. EEZ waters surrounding the Hawaiian 

Islands (Barlow 2003; see Appendix 2 for details on timing and 

location of survey effort). Outer line represents approximate 

boundary of survey area and U.S. EEZ. 

223
POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size 

(7,078) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.50 

(for a species of unknown status with no known fishery mortality; Wade and Angliss 1997), resulting in a PBR of 

71 striped dolphins per year. 

 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

Information on fishery-related mortality and serious injury of cetaceans in Hawaiian waters is limited, but 

the gear types used in Hawaiian fisheries are responsible for marine mammal mortality and serious injury in other 

fisheries throughout U.S. waters. Gillnets appear to capture marine mammals wherever they are used, and float lines 

from lobster traps and longlines can be expected to occasionally entangle whales (Perrin et al. 1994a). 

 Interactions with cetaceans have been reported for all Hawaiian pelagic fisheries (Nitta and Henderson 

1993), but no interactions with striped dolphins have been documented. None were observed hooked or entangled in 

the Hawaii-based longline fishery between 1994 and 2002, with approximately 4-25% of all effort observed (Forney 

2004). Interaction rates between dolphins and the NWHI bottomfish fishery have been estimated based on studies 

conducted in 1990-1993, indicating that an average of 2.67 dolphin interactions, most likely involving bottlenose 

and rough-toothed dolphins, occurred for every 1000 fish brought on board (Kobayashi and Kawamoto 1995). 

Fishermen claim interactions with dolphins who steal bait and catch are increasing. It is not known whether these 

interactions result in serious injury or mortality of dolphins, nor whether striped dolphins are involved. 

STATUS OF STOCK 

The status of striped dolphins in Hawaiian waters relative to OSP is unknown, and there are insufficient 

data to evaluate trends in abundance. No habitat issues are known to be of concern for this species. They are not 

listed as “threatened” or “endangered” under the Endangered Species Act (1973), nor as “depleted” under the 

MMPA. The Hawaiian stock of striped dolphins is not considered strategic under the 1994 amendments to the 

MMPA given the absence of reported fisheries related mortality. Insufficient information is available to determine 

whether the total fishery mortality and serious injury for striped dolphins is insignificant and approaching zero 

mortality and serious injury rate. 

REFERENCES

Barlow, J. 2003. Cetacean abundance in Hawaiian waters during summer/fall 2002. Admin. Rep. LJ-03-13. 

Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La 

Jolla, CA 92037. 

Dizon, A. E., W. F. Perrin, and P. A. Akin. 1994. Stocks of dolphins (Stenella spp. and Delphinus delphis) in the 

eastern tropical Pacific: a phylogeographic classification. NOAA Tech. Rep. NMFS 119, 20 pp. 

Forney, K.A. 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994_2002. 

Admin. Rep. LJ-04-07. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92037. 17 pp. 

Kishiro, T. and T. Kasuya. 1993. Review of Japanese dolphin drive fisheries and their status. Rep. Int. Whal. 

Commn. 43:439-452. 

Kobayashi, D. R. and K. E. Kawamoto. 1995. Evaluation of shark, dolphin, and monk seal interactions with 

Northwestern Hawaiian Island bottomfishing activity: a comparison of two time periods and an estimate of 

economic impacts. Fisheries Research 23: 11-22. 

Maldini, D., L. Mazzuca, and S. Atkinson. 2005. Odontocete stranding patterns in the Main Hawaiian Islands 

(1937-2002): How do they compare with live animal surveys? Pacific Science 59(1):55-67. 

Miyashita, T. 1993. Abundance of dolphin stocks in the western North Pacific taken by the Japanese drive fishery. 

Rep. Int. Whal. Commn. 43:417-437. 

Mobley, J. R. , Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and 

abundance of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. 

Rep. LJ-00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 26 pp. 

Nitta, E. 1991. The marine mammal stranding network for Hawaii: an overview. In: J.E. Reynolds III, D.K. Odell 

(eds.), Marine Mammal Strandings in the United States, pp.56-62. NOAA Tech. Rep. NMFS 98, 157 pp. 

Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

224
Perrin, W.F., G. P. Donovan and J. Barlow. 1994a. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Special Issue 

15, 629 pp. 

Perrin, W. F., C. E. Wilson, and F. I. Archer, II. 1994b. Striped dolphin Stenella coeruleoalba (Meyen, 1833). In: 

S. H. Ridgway and R. Harrison (eds.), Handbook of Marine Mammals, Vol.5: The First Book of Dolphins, 

pp 129-159. Academic Press, 416 pp. 

Shallenberger, E.W. 1981. The status of Hawaiian cetaceans. Final report to U.S. Marine Mammal Commission. 

MMC-77/23, 79pp. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

Wade, P. R. and T. Gerrodette. 1993. Estimates of cetacean abundance and distribution in the eastern tropical 

Pacific. Rep. Int. Whal. Commn. 43:477-493. 

225
Revised 03/15/2005 

FRASER'S DOLPHIN (Lagenodelphis hosei): 

Hawaiian Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

Fraser’s dolphins are distributed 

worldwide in tropical waters (Perrin et al. 

1994b). They have only recently been 

documented within the U.S. Exclusive 

Economic Zone (EEZ) of the Hawaiian 

Islands, during a 2002 cetacean survey 

(Barlow 2003, Figure 1). No strandings 

of Fraser’s dolphins have been 

documented in the Hawaiian Islands 

(Nitta 1991; Maldini 2005). For the 

Marine Mammal Protection Act (MMPA) 

stock assessment reports, there is a single 

Pacific management stock including only 

animals found within the U.S. EEZ of the 

Hawaiian Islands. 

POPULATION SIZE

 Population estimates for Fraser’s 

dolphins have been made in the eastern 

tropical Pacific (Wade and Gerrodette 

1993), but it is not known whether these 

animals are part of the same population 

that occurs around the Hawaiian Islands 

and in the central North Pacific. No 

sightings of this species were made 

during twelve aerial surveys, conducted as part of the Marine Mammal Research Program of the Acoustic 

Thermometry of Ocean Climate (ATOC) study, within about 25 nmi of the main Hawaiian Islands in 1993, 1995 

and 1998 (Mobley et al. 2000). A 2002 shipboard line-transect survey of the entire Hawaiian Islands EEZ resulted in 

an abundance estimate of 16,836 (CV=1.11) Fraser’s dolphins (Barlow 2003). This is currently the best available 

abundance estimate for this stock. 

Minimum Population Estimate

 The log-normal 20th percentile of the 2002 abundance estimate is 7,917 Fraser’s dolphins. 

Current Population Trend

 No data are available on current population trend. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No data are available on current or maximum net productivity rate for the Hawaiian stock of Fraser’s 

dolphin. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock of Fraser’s dolphin is calculated as the 

minimum population size (7,917) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times

a recovery factor of 0.50 (for a stock of unknown status with no known fishery mortality or serious injury within the 

Hawaiian Islands EEZ; Wade and Angliss 1997), resulting in a PBR of 79 Fraser’s dolphins per year. 

W180 W175 W170 W165 W160 W155 W150

N10

N15

N20

N25

N30

N35

Figure 1. Fraser’s dolphin sighting locations during the 2002 

shipboard cetacean survey of U.S. waters surrounding the Hawaiian 

Islands (Barlow 2003; see Appendix 2 for details on timing and 

location of survey effort). Outer line indicates approximate boundary 

of survey area and U.S. EEZ.

226
HUMAN CAUSED MORTALITY AND SERIOUS INJURY 

Fishery Information

 Information on fishery-related mortality and serious injury of cetaceans in Hawaiian waters is limited, but 

the gear types used in Hawaiian fisheries are responsible for marine mammal mortality and serious injury in other 

fisheries throughout U.S. waters. Gillnets appear to capture marine mammals wherever they are used, and float lines 

from lobster traps and longlines can be expected to occasionally entangle whales (Perrin et al. 1994a). Interactions 

with cetaceans have been reported for all Hawaiian pelagic fisheries (Nitta and Henderson 1993), but none of these 

interactions are known to have involved Fraser’s dolphins. None were observed hooked or entangled in the Hawaiibased longline fishery between 1994 and 2002, with approximately 4-25% of all effort observed (Forney 2004). 

Interaction rates between dolphins and the NWHI bottomfish fishery have been estimated based on studies 

conducted in 1990-1993, indicating that an average of 2.67 dolphin interactions, most likely involving bottlenose 

and rough-toothed dolphins, occurred for every 1000 fish brought on board (Kobayashi and Kawamoto 1995). 

Fishermen claim interactions with dolphins who steal bait and catch are increasing. It is not known whether these 

interactions result in serious injury or mortality of dolphins, nor whether Fraser’s dolphins are involved. 

STATUS OF STOCK 

 The status of Fraser's dolphins in Hawaiian waters relative to OSP is unknown, and there are insufficient 

data to evaluate trends in abundance. No habitat issues are known to be of concern for this species. They are not 

listed as “threatened” or “endangered” under the Endangered Species Act (1973), nor as “depleted” under the 

MMPA. The Hawaiian stock of Fraser’s dolphins is not considered strategic under the 1994 amendments to the 

MMPA, because there has been no reported fisheries related mortality or serious injury within the U.S. EEZ of the 

Hawaiian Islands. Insufficient information is available to determine whether the total fishery mortality and serious 

injury for Fraser’s dolphins is insignificant and approaching zero mortality and serious injury rate. 

REFERENCES

Barlow, J. 2003. Cetacean abundance in Hawaiian waters during summer/fall 2002. Admin. Rep. LJ-03-13. 

Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La 

Jolla, CA 92037. 

Forney, K.A. 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994_2002. 

Admin. Rep. LJ-04-07. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92037. 17 pp. 

Kobayashi, D. R. and K. E. Kawamoto. 1995. Evaluation of shark, dolphin, and monk seal interactions with 

Northwestern Hawaiian Island bottomfishing activity: a comparison of two time periods and an estimate of 

economic impacts. Fisheries Research 23: 11-22. 

Maldini, D., L. Mazzuca, and S. Atkinson. 2005. Odontocete stranding patterns in the Main Hawaiian Islands 

(1937-2002): How do they compare with live animal surveys? Pacific Science 59(1):55-67. 

Mobley, J. R. , Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and 

abundance of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. 

Rep. LJ-00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 26 pp. 

Nitta, E. 1991. The marine mammal stranding network for Hawaii: an overview. In: J.E. Reynolds III, D.K. Odell 

(eds.), Marine Mammal Strandings in the United States, pp.56-62. NOAA Tech. Rep. NMFS 98, 157 pp. 

Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

Perrin, W.F., G. P. Donovan and J. Barlow. 1994a. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Special Issue 

15, 629 pp. 

Perrin, W.F., S. Leatherwood and A. Collet. 1994b. Fraser’s dolphin Lagenodelphis hosei (Fraser 1956). Pages 

225-240 In: S. H. Ridgway and R. Harrison (eds) Handbook of Marine Mammals, Vol. 5: The first book of 

dolphins. Academic Press, London. 416 pp. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

Workshop April 3-5, 1996, Seattle, Washington. U. S. Dept. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

Wade, P. R. and T. Gerrodette. 1993. Estimates of cetacean abundance and distribution in the eastern tropical 

Pacific. Rep. Int. Whal. Commn. 43:477-493. 

227
Revised 03/15/2005

MELON-HEADED WHALE (Peponocephala electra): 

Hawaiian Stock

STOCK DEFINITION AND GEOGRAPHIC RANGE

 Melon-headed whales are found 

in tropical and warm-temperate waters 

throughout the world. The distribution 

of reported sightings suggests that the 

oceanic habitat of this species is 

primarily equatorial waters (Perryman et 

al. 1994). Small numbers have been 

taken in the eastern tropical Pacific, and 

they are occasionally killed in direct 

fisheries in Japan and elsewhere in the 

western Pacific. Large herds are seen 

regularly in Hawaiian waters, especially 

off the Waianae coast of Oahu, the north 

Kohala coast of Hawaii, and the leeward 

coast of Lanai (Shallenberger 1981). A 

comprehensive shipboard survey of the 

Hawaiian Exclusive Economic Zone 

(EEZ), resulted in only one sighting of 

melon-headed whales (Figure 1; Barlow 

2003). Inter-island movements from 

Kauai to Hawaii have been documented 

and genetic samples from at least 82 

animals are available for future stock 

structure analyses (R.W. Baird, pers. 

comm.). Little is known about this 

species elsewhere in its range, and most knowledge about its biology comes from mass strandings (Perryman et al. 

1994). Fourteen strandings are known from Hawaii (Nishiwaki and Norris 1966; Shallenberger 1981; Nitta 1991; 

Maldini 2005). For the Marine Mammal Protection Act (MMPA) stock assessment reports, there is a single Pacific 

management stock including only animals found within the U.S. EEZ of the Hawaiian Islands. 

POPULATION SIZE

 An abundance estimate of melon-headed whales is available for the eastern tropical Pacific (Wade and 

Gerrodette 1993), but it is not known whether any of these animals are part of the same population that occurs 

around the Hawaiian Islands. As part of the Marine Mammal Research Program of the Acoustic Thermometry of 

Ocean Climate (ATOC) study, a total of twelve aerial surveys were conducted within about 25 nmi of the main 

Hawaiian Islands in 1993, 1995 and 1998. An abundance estimate of 154 (CV=0.88) melon-headed whales was 

calculated from the combined survey data (Mobley et al. 2000). This study underestimated the total number of 

melon-headed whales within the U.S. EEZ off Hawaii, because areas around the Northwestern Hawaiian Islands 

(NWHI) and beyond 25 nautical miles from the main islands were not surveyed. Furthermore, the data on which 

this estimate was based are now over 5 years old. A 2002 shipboard line-transect survey of the entire Hawaiian 

Islands EEZ resulted in an abundance estimate of 2,947 (CV=1.11) melon-headed whales (Barlow 2003). This is 

currently the best available abundance estimate for this stock. 

Minimum Population Estimate

 The log-normal 20th percentile of the 2002 abundance estimate is 1,386 melon-headed whales. 

Current Population Trend

 No data are available on current population trend. 

W180 W175 W170 W165 W160 W155 W150

N10

N15

N20

N25

N30

N35

Figure 1. Melon-headed whale sighting location during the 2002 

shipboard survey of U.S. EEZ waters surrounding the Hawaiian 

Islands (Barlow 2003; see Appendix 2 for details on timing and 

location of survey effort). Outer line represents approximate 

boundary of survey area and U.S. EEZ. 

228
CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No data are available on current or maximum net productivity rate. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size 

(1,386) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.50 

(for a species of unknown status with no known fishery mortality; Wade and Angliss 1997), resulting in a PBR of 14 

melon-headed whales per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY 

Fishery Information

 Information on fishery-related mortality and serious injury of cetaceans in Hawaiian waters is limited, but 

the gear types used in Hawaiian fisheries are responsible for marine mammal mortality and serious injury in other 

fisheries throughout U.S. waters. Gillnets appear to capture marine mammals wherever they are used, and float lines 

from lobster traps and longlines can be expected to occasionally entangle whales (Perrin et al. 1994). 

 Interactions with cetaceans have been reported for all Hawaiian pelagic fisheries (Nitta and Henderson 

1993), but no interactions with melon-headed whales have been documented. None were observed hooked in the 

Hawaii-based longline fishery between 1994 and 2002, with approximately 4-25% of all effort observed (Forney 

2004). Interaction rates between dolphins and the NWHI bottomfish fishery have been estimated based on studies 

conducted in 1990-1993, indicating that an average of 2.67 dolphin interactions, most likely involving bottlenose 

and rough-toothed dolphins, occurred for every 1000 fish brought on board (Kobayashi and Kawamoto 1995). 

Fishermen claim interactions with dolphins who steal bait and catch are increasing. It is not known whether these 

interactions result in serious injury or mortality of dolphins, nor whether melon-headed whales are involved. 

STATUS OF STOCK

 The status of melon-headed whales in Hawaiian waters relative to OSP is unknown, and there are 

insufficient data to evaluate trends in abundance. No habitat issues are known to be of concern for this species. 

They are not listed as “threatened” or “endangered” under the Endangered Species Act (1973), nor as “depleted” 

under the MMPA. The Hawaiian stock of melon-headed whales is not considered strategic under the 1994 

amendments to the MMPA given the absence of reported fisheries related mortality or serious injury. Insufficient 

information is available to determine whether the total fishery mortality and serious injury for melon-headed whales 

is insignificant and approaching zero mortality and serious injury rate. 

REFERENCES 

Barlow, J. 2003. Cetacean abundance in Hawaiian waters during summer/fall 2002. Admin. Rep. LJ-03-13. 

Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La 

Jolla, CA 92037. 

Forney, K.A. 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994-2002. 

Admin. Rep. LJ-04-07. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92037. 17 pp. 

Kobayashi, D. R. and K. E. Kawamoto. 1995. Evaluation of shark, dolphin, and monk seal interactions with 

Northwestern Hawaiian Island bottomfishing activity: a comparison of two time periods and an estimate of 

economic impacts. Fisheries Research 23:11-22. 

Maldini, D., L. Mazzuca, and S. Atkinson. 2005. Odontocete stranding patterns in the Main Hawaiian Islands 

(1937-2002): How do they compare with live animal surveys? Pacific Science 59(1):55-67. 

Mobley, J. R. , Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and 

abundance of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. 

Rep. LJ-00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 26 pp. 

Nishiwaki, M. and K. S. Norris. 1966. A new genus, Peponocephala, for the odontocete cetacean species Electra 

electra. Sci. Rep. Whales Res. Inst. 20:95-100. 

Nitta, E. 1991. The marine mammal stranding network for Hawaii: an overview. In: J.E. Reynolds III, D.K. Odell 

(eds.), Marine Mammal Strandings in the United States, pp.56-62. NOAA Tech. Rep. NMFS 98, 157 pp. 

Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

229
Perrin, W.F., G. P. Donovan and J. Barlow. 1994. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Special Issue 

15, 629 pp. 

Perryman, W. L., D. W. K. Au, S. Leatherwood, and T. A. Jefferson. 1994. Melon-headed whale Peponocephala 

electra Gray, 1846. In: S. H. Ridgway and R. Harrison (eds.), Handbook of Marine Mammals, Vol.5: The 

First Book of Dolphins, pp. 363-386. Academic Press, 416 pp. 

Shallenberger, E.W. 1981. The status of Hawaiian cetaceans. Final report to U.S. Marine Mammal Commission. 

MMC-77/23, 79pp. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

Wade, P. R. and T. Gerrodette. 1993. Estimates of cetacean abundance and distribution in the eastern tropical 

Pacific. Rep. Int. Whal. Commn. 43:477-493.

230
Revised 03/15/2005

PYGMY KILLER WHALE (Feresa attenuata): 

Hawaiian Stock

STOCK DEFINITION AND GEOGRAPHIC RANGE

 Pygmy killer whales are found 

in tropical and subtropical waters 

throughout the world (Ross and 

Leatherwood 1994). They are poorly 

known in most parts of their range. 

Small numbers have been taken directly 

and incidentally in both the western and 

eastern Pacific. Most knowledge of this 

species is from stranded or live-captured 

specimens. Pryor et al. (1965) stated 

that pygmy killer whales have been 

observed several times off the lee shore 

of Oahu, and that "they seem to be 

regular residents of the Hawaiian area." 

Although all sightings up to that time 

had been off Oahu and the Big Island, 

Shallenberger (1981) stated that this 

species might be found elsewhere in 

Hawaii, as well. No pygmy killer 

whales were seen during 1993-98 aerial 

surveys within about 25 nmi of the main 

Hawaiian Islands (Mobley et al. 2000). 

Three sightings of pygmy killer whales 

were made during a 2002 shipboard 

survey of U.S. Exclusive Economic 

Zone (EEZ) waters surrounding the Hawaiian Islands (Figure 1; Barlow 2003). Six strandings have been 

documented from Maui and the island of Hawaii (Nitta 1991, Maldini 2005). For the Marine Mammal Protection 

Act (MMPA) stock assessment reports, there is a single Pacific management stock including only animals found 

within the U.S. EEZ of the Hawaiian Islands. 

POPULATION SIZE

 A population estimate has been made for this species in the eastern tropical Pacific (Wade and Gerrodette 

1993), but it is not known whether any of these animals are part of the same population that occurs around the 

Hawaiian Islands. As part of the Marine Mammal Research Program of the Acoustic Thermometry of Ocean 

Climate (ATOC) study, a total of twelve aerial surveys were conducted within about 25 nmi of the main Hawaiian 

Islands in 1993, 1995 and 1998 (Mobley et al. 2000), but there were no sightings of pygmy killer whales. A 2002 

shipboard line-transect survey of the entire Hawaiian Islands EEZ resulted in an abundance estimate of 817 

(CV=1.12) pygmy killer whales (Barlow 2003). This is currently the best available abundance estimate for this 

stock. 

Minimum Population Estimate

 The log-normal 20th percentile of the 2002 abundance estimate is 382 pygmy killer whales. 

Current Population Trend

 No data are available on current population trend. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No data are available on current or maximum net productivity rate. 

W180 W175 W170 W165 W160 W155 W150

N10

N15

N20

N25

N30

N35

Figure 1. Pygmy killer whale sighting locations during the 2002 

shipboard survey of U.S. EEZ waters surrounding the Hawaiian 

Islands (Barlow 2003; see Appendix 2 for details on timing and 

location of survey effort). Outer line represents approximate 

boundary of survey area and U.S. EEZ. 

231
POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size 

(382) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.50 

(for a stock of unknown status with no known fishery mortality or serious injury within the Hawaiian Islands EEZ; 

Wade and Angliss 1997), resulting in a PBR of 3.8 pygmy killer whales per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

Information on fishery-related mortality and serious injury of cetaceans in Hawaiian waters is limited, but 

the gear types used in Hawaiian fisheries are responsible for marine mammal mortality and serious injury in other 

fisheries throughout U.S. waters. Gillnets appear to capture marine mammals wherever they are used, and float lines 

from lobster traps and longlines can be expected to occasionally entangle whales (Perrin et al. 1994). 

 Interactions with cetaceans have been reported for all Hawaiian pelagic fisheries (Nitta and Henderson 

1993), but no interactions with pygmy killer whales have been documented. None were observed hooked or 

entangled in the Hawaii-based longline fishery between 1994 and 2002, with approximately 4-25% of all effort 

observed (Forney 2004). Interaction rates between dolphins and the NWHI bottomfish fishery have been estimated 

based on studies conducted in 1990-1993, indicating that an average of 2.67 dolphin interactions, most likely 

involving bottlenose and rough-toothed dolphins, occurred for every 1000 fish brought on board (Kobayashi and 

Kawamoto 1995). Fishermen claim interactions with dolphins who steal bait and catch are increasing. It is not 

known whether these interactions result in serious injury or mortality of dolphins, nor whether pygmy killer whales 

are involved. 

STATUS OF STOCK

 The status of pygmy killer whales in Hawaiian waters relative to OSP is unknown, and there are 

insufficient data to evaluate trends in abundance. No habitat issues are known to be of concern for this species. This 

species is not listed as “threatened” or “endangered” under the Endangered Species Act (1973), nor as “depleted” 

under the MMPA. The Hawaiian stock of pygmy killer whales is not considered strategic under the 1994 

amendments to the MMPA given the absence of reported fisheries related mortality or serious injury. Insufficient 

information is available to determine whether the total fishery mortality and serious injury for pygmy killer whales 

is insignificant and approaching zero mortality and serious injury rate. 

REFERENCES 

Barlow, J. 2003. Cetacean abundance in Hawaiian waters during summer/fall 2002. Admin. Rep. LJ-03-13. 

Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La 

Jolla, CA 92037. 

Forney, K.A. 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994-2002. 

Admin. Rep. LJ-04-07. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92037. 17 pp. 

Kobayashi, D. R. and K. E. Kawamoto. 1995. Evaluation of shark, dolphin, and monk seal interactions with 

Northwestern Hawaiian Island bottomfishing activity: a comparison of two time periods and an estimate of 

economic impacts. Fisheries Research 23: 11-22. 

Maldini, D., L. Mazzuca, and S. Atkinson. 2005. Odontocete stranding patterns in the Main Hawaiian Islands 

(1937-2002): How do they compare with live animal surveys? Pacific Science 59(1):55-67. 

Mobley, J. R. , Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and 

abundance of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. 

Rep. LJ-00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 26 pp. 

Nitta, E. 1991. The marine mammal stranding network for Hawaii: an overview. In: J.E. Reynolds III, D.K. Odell 

(eds.), Marine Mammal Strandings in the United States, pp.56-62. NOAA Tech. Rep. NMFS 98, 157 pp. 

Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

Perrin, W.F., G. P. Donovan and J. Barlow. 1994. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Special Issue 

15, 629 pp. 

Pryor, T., K. Pryor and K. S. Norris. 1965. Observations on a pygmy killer whale (Feresa attenuata Gray) from 

Hawaii. J. Mamm. 46:450-461. 

232
Ross, G. J. B. and S. Leatherwood. 1994. Pygmy killer whale Feresa attenuata Gray, 1874. In: S. H. Ridgway and 

R. Harrison (eds.), Handbook of Marine Mammals, Vol.5: The First Book of Dolphins, pp.387-404. 

Academic Press, 416 pp. 

Shallenberger, E.W. 1981. The status of Hawaiian cetaceans. Final report to U.S. Marine Mammal Commission. 

MMC-77/23, 79pp. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

Wade, P. R. and T. Gerrodette. 1993. Estimates of cetacean abundance and distribution in the eastern tropical 

Pacific. Rep. Int. Whal. Commn. 43:477-493. 

233
Revised 10/30/2007 

FALSE KILLER WHALE (Pseudorca crassidens): 

Pacific Islands Region Stock Complex - Hawaii & Palmyra Atoll

STOCK DEFINITIONS AND GEOGRAPHIC RANGES

False killer whales are found 

worldwide mainly in tropical and warmtemperate waters (Stacey et al. 1994). In the 

North Pacific, this species is well known from

southern Japan, Hawaii, and the eastern tropical

Pacific. There are six stranding records from

Hawaiian waters (Nitta 1991; Maldini 2005). 

One on-effort sighting of false killer whales was 

made during a 2002 shipboard survey of waters

within the U.S. Exclusive Economic Zone

(EEZ) of the Hawaiian Islands (Figure 1;

Barlow 2006). Smaller-scale surveys conducted

around the Main Hawaiian Islands (Figure 2)

show that false killer whales are also commonly 

encountered in nearshore waters (Baird et al. 

2005, Mobley et al. 2000, Mobley 2001, 2002,

2003, 2004). This species also occurs in U.S. 

EEZ waters around Palmyra Atoll (Figure 1)

and sightings of false killer whales have been

recently confirmed within the Johnston Atoll 

EEZ (NMFS/PIR/PSD unpublished data) and 

the U.S. EEZ waters of American Samoa

(NOS/HIHWNMS unpublished data). 

180

o 170o 160o 150o 140o

Longitude (W)

0

o

10o

20o

30o

Latitude (N)

Johnston

Atoll

Palmyra Atoll

Jarvis I

Howland & 

Baker Is

Hawaiian

Islands

Figure 1. False killer whale sighting locations during standardized

shipboard surveys of the Hawaiian U.S. EEZ (2002, black diamond, 

Barlow 2006), the Palmyra U.S. EEZ (2005, open squares, Barlow and

Rankin 2007), and pelagic waters of the central Pacific south of the 

Hawaiian Islands (2005, open squares, Barlow and Rankin 2007). Outer 

lines represent approximate boundary of U.S. EEZs.

Figure 2. False killer whale sighting locations during 2000-2004 boatbased surveys (+) (Baird et al. 2005) and 1993-2003 aerial surveys (•) 

(Mobley et al. 2000, Mobley 2001, 2002, 2003, 2004) around the Main

Hawaiian Islands. See Appendix 2 for details on timing and location of

survey effort.

Genetic analyses of tissue samples 

collected within the Eastern North Pacific 

(ENP) indicate restricted gene flow between

false killer whales sampled near the main

Hawaiian Islands and false killer whales 

sampled in all other regions of the ENP

(Chivers et al. 2007). False killer whales

sampled at Palmyra Atoll appear more closely 

related to animals sampled in the waters of the 

pelagic ENP, Panama and Mexico (Chivers et

al. 2007). Thus, false killer whales occurring 

near Palmyra Atoll may be part of a larger

population inhabiting a broad geographic area

within the central and eastern North Pacific. 

Since 2003, observers of the Hawaiibased longline fishery have also been collecting 

tissue samples of caught cetaceans for genetic 

analysis whenever possible. Four false killer 

whale samples, two collected outside the

Hawaiian EEZ and two collected more than 100 

nautical miles from the main Hawaiian Islands

(See Figure 3) were determined to have ENPlike haplotypes. This indicates that false killer

whales within the Hawaiian EEZ belong to two 

different genetic populations, with a boundary

somewhere within the Hawaiian EEZ. Both 

genetic types are provisionally included within a

single Hawaiian stock for assessment purposes.

234
Efforts are currently underway to obtain and analyze additional tissue samples of false killer whales for further 

studies of population structure in the North Pacific Ocean. 

For the Marine Mammal Protection Act (MMPA) stock assessment reports, there are currently two Pacific 

Islands Region management stocks: 1) the Hawaii stock, which includes animals found within the U.S. EEZ of the 

Hawaiian Islands, and 2) the Palmyra Stock, which includes false killer whales found with the U.S. EEZ of Palmyra 

Atoll. Estimates of abundance, potential biological removal, and status determinations will be presented separately 

for U.S. EEZ waters of the Hawaiian Islands and Palmyra Atoll. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY 

Fishery Information 

Interactions with cetaceans have been reported for Hawaiian pelagic fisheries, and false killer whales have 

been identified in fishermen's logs and NMFS observer records as taking catches from pelagic longlines (Nitta and 

Henderson 1993, NMFS/PIR unpublished data). They have also been observed feeding on mahi mahi, Coryphaena 

hippurus, and yellowfin tuna, Thunnus albacares, and they have been reported to take large fish (up to 70 pounds) 

from the trolling lines of both commercial and recreational fishermen (Shallenberger 1981). 

 Between 1994 and 2005, 20 false killer whales were observed hooked or entangled in the Hawaii-based 

longline fishery, with approximately 4-34% of all effort observed (Table 1; Forney and Kobayashi 2007). Twelve 

additional unidentified cetaceans, which may have been false killer whales based on the observer's descriptions, 

were also taken (hooked or entangled) in this fishery, but were not included in this analysis (Figure 3; Forney and 

Kobayashi 2007). During 24,542 observed sets, the average interaction rate of false killer whales was 0.81 false 

killer whales per 1,000 sets. Two of the false killer whales were killed, and all others caught were considered 

seriously injured, based on an evaluation of the observer’s description of the interaction (Forney and Kobayashi, in 

press) and following established guidelines for assessing serious injury in marine mammals (Angliss and DeMaster 

1998). Average 5-yr estimates of annual mortality and serious injury for 2001-2005 are 7.7 (CV = 0.34) false killer 

whales outside of U.S. EEZs, 4.9 (CV = 0.41) within the Hawaiian Islands EEZ, and 1.9 (CV = 0.59) within the 

EEZ of Palmyra Atoll (Table 1). Total estimated annual mortality and serious injury for all U.S. EEZs combined 

averaged 6.8 (CV = 0.34) between 2001 and 2005. Since 2001, the Hawaii-based longline fishery has undergone a 

series of regulatory changes, primarily to protect sea turtles (NMFS 2001). Potential impacts of these regulatory 

changes on the rate of false killer whale interactions are unknown. 

Table 1. Summary of available information on incidental mortality and serious injury of false killer whales (Pacific 

Islands Stock Complex) in commercial fisheries, within and outside of selected U.S. EEZs (Forney and Kobayashi, 

in press). Mean annual takes are based on 2001-2005 data unless otherwise indicated. 

Observed and estimated mortality and serious injury of false killer whales, by EEZ region

Outside of U.S. EEZs Hawaiian Islands EEZ Palmyra Atoll EEZ Fishery 

Name Year Data 

Type

Percent 

Observer 

Coverage

Obs.

Estimat d e

(CV)

Mean 

Annual 

Takes 

(CV)

Obs.

Estimated 

(CV)

Mean 

Annual 

Takes 

(CV)

Obs. Estimated 

(CV)

Mean 

Annual 

Takes 

(CV)

Hawaiibased 

longline 

fishery 

 2001 

2002 

2003 

2004 

2005 

observer 

data

23.0% 

24.8% 

21.9% 

25.4% 

34.2% 

2 

3 

0 

3 

1 

 11 (0.71) 

 12 (0.58) 

0 (-) 

12 (0.58) 

4 (1.00) 

 7.7 

(0.34) 

0 

0 

2 

3 

1 

0 (-) 

0 (-) 

8 ( 0.68) 

13 (0.58) 

3 (1.00) 

4.9 

(0.41) 

1 

2 

0 

0 

0 

4 (1.00) 

5 (0.71) 

0 (-) 

0 (-) 

0 (-) 

1.9 

 (0.59)

Minimum total annual takes within U.S. EEZ waters 6.8 (0.34)

HAWAII STOCK

POPULATION SIZE

 A recent mark-recapture study of photo-identification data obtained during 2000-2004 around the main 

Hawaiian Islands produced an estimate of 123 (CV=0.72) false killer whales (Baird et al. 2005). Analyses of a 2002 

shipboard line-transect survey of the entire Hawaiian Islands EEZ (HICEAS survey) resulted in an abundance 

estimate of 236 (CV=1.13) false killer whales (Barlow 2006). A recent re-analysis of the HICEAS data using 

improved methods and incorporating additional sighting information obtained on line-transect surveys south of the 

Hawaiian EEZ during 2005, resulted in a revised estimate of 484 (CV = 0.93) false killer whales within the 

Hawaiian Islands EEZ (Barlow & Rankin 2007). This is the best available abundance estimate for false killer 

whales within the Hawaiian Islands EEZ. 

235
 

Minimum Population Estimate

The log-normal 20th percentile of the 2002 abundance estimate for the Hawaiian Islands EEZ (Barlow & 

Rankin 2007) is 249 false killer whales. 

Current Population Trend

No data are available on current population trend. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

No data are available on current or maximum net productivity rate for this species in Hawaiian waters. 

POTENTIAL BIOLOGICAL REMOVAL

The potential biological removal

(PBR) level for the Hawaiian false killer whale

stock is calculated as the minimum population 

size (249) times one half the default maximum

net growth rate for cetaceans (1⁄2 of 4%) times

a recovery factor of 0.48 (for a stock of

unknown status with a Hawaiian Islands EEZ 

mortality and serious injury rate CV between

0.30 and 0.60; Wade and Angliss 1997),

resulting in a PBR of 2.4 false killer whales 

per year. 

STATUS OF STOCK

The status of false killer whales in 

Hawaiian waters relative to OSP is unknown, 

and there are insufficient data to evaluate

trends in abundance. No habitat issues are 

known to be of concern for this species. They 

are not listed as “threatened” or “endangered”

under the Endangered Species Act (1973), nor

as “depleted” under the MMPA. Because the 

rate of mortality and serious injury to false 

killer whales within the Hawaiian Islands EEZ 

in the Hawaii-based longline fishery (4.9 

animals per year) exceeds the PBR (2.4), this 

stock is considered a “strategic stock” under 

the 1994 amendments to the MMPA. The total 

fishery mortality and serious injury for 

Hawaiian false killer whales cannot be considered to be insignificant and approaching zero, because it exceeds the 

PBR. Furthermore, additional injury and mortality of false killer whales is known to occur in longline fishing

operations in international waters, and the potential effect on the Hawaiian Islands EEZ stock is unknown. 

180o 170o 160o 150o 140o

Longitude (W)

0

o

10o

20o

30o

Latitude (N)

Johnston

Atoll

Palmyra Atoll

Jarvis I

Howland & 

Baker Is

Hawaiian

Islands

Figure 3. Locations of observed false killer whale takes (filled

symbols) and possible takes of this species (open symbols) in

the Hawaii-based longline fishery, 1994-2003. Stars are 

locations of genetic samples from fishery-caught false killer

whales. Solid lines represent the U.S. EEZ. Set locations in this

fishery are summarized in Appendix 1.

PALMYRA STOCK

POPULATION SIZE

Recent line transect surveys in the U.S. EEZ waters of Palmyra Atoll produced an estimate of 1,329 (CV =

0.65) false killer whales (Barlow & Rankin 2007). This is the best available abundance estimate for false killer 

whales within the Palmyra Atoll EEZ. 

Minimum Population Estimate

The log-normal 20th percentile of the 2002 abundance estimate for the Palmyra Atoll EEZ (Barlow &

Rankin 2007) is 806 false killer whales. 

Current Population Trend

No data are available on current population trend. 

236
CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No data are available on current or maximum net productivity rate for this species in Palmyra Atoll waters. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for the Palmyra Atoll false killer whale stock is calculated as 

the minimum population size (806) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) 

times a recovery factor of 0.48 (for a stock of unknown status with a mortality and serious injury rate CV between 

0.30 and 0.60; Wade and Angliss 1997), resulting in a PBR of 7.7 false killer whales per year. 

STATUS OF STOCK

 The status of false killer whales in Palmyra Atoll EEZ waters relative to OSP is unknown, and there are 

insufficient data to evaluate trends in abundance. No habitat issues are known to be of concern for this species. 

They are not listed as “threatened” or “endangered” under the Endangered Species Act (1973), nor as “depleted” 

under the MMPA. The rate of mortality and serious injury to false killer whales within the Palmyra Atoll EEZ in 

the Hawaii-based longline fishery (1.9 animals per year) does not exceed the PBR (7.7) for this stock and thus, this 

stock is not considered “strategic” under the 1994 amendments to the MMPA. The total fishery mortality and 

serious injury for Palmyra Atoll false killer whales is greater than 10% of the PBR and, therefore, cannot be 

considered to be insignificant and approaching zero. Additional injury and mortality of false killer whales is known 

to occur in longline fishing operations in international waters, and the potential effect on the Palmyra stock is 

unknown. 

REFERENCES

Angliss, R. P. and D. P. DeMaster. 1998. Differentiating Serious and Non-Serious Injury of Marine Mammals 

Taken Incidental to Commercial Fishing Operations: Report of the Serious Injury Workshop 1_2 April 

1997, Silver Spring, Maryland. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR-13. 48 pp. 

Baird, R. W., Ligon, A. D., Hooker, S. K., and A. M. Gorgone. 2001. Subsurface and nighttime behaviour of 

pantropical spotted dolphins in Hawai’i. Can. J. Zool. 79:988-996. 

Baird, R.W., McSweeney D.J., Webster, D.L., Gorgone, A.M., and Ligon, A.D. 2003. Studies of odontocete 

population structure in Hawaiian waters: Results of a survey through the main Hawaiian Islands in May 

and June 2003. Report prepared under contract #AB133F-02-CN-0106 to the Southwest Fisheries Science 

Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 92037, USA. 10p. 

Baird, R.W., A.M. Gorgone, D.L. Webster, D.J. McSweeney, J.W. Durban, A.D. Ligon, D.R. Salden, and M.H. 

Deakos. 2005. False killer whales around the Main Hawaiian Islands: An assessment of inter-island 

movements and population size using individual photo-identification. Contract Report JJ133F04SE0120 

prepared for the Pacific Islands Fisheries Science Center, National Marine Fisheries Service, 2570 Dole 

Street, Honolulu, Hawaii, 96822. 24pp. 

Barlow, J. 2006. Cetacean abundance in Hawaiian waters estimated from a summer/fall survey in 2002. Marine 

Mammal Science 22: 446–464. 

Barlow, J. and S. Rankin. 2007. False killer whale abundance and density: Preliminary estimates for the PICEAS 

study area south of Hawaii and new estimates for the US EEZ around Hawaii. Administrative Report LJ07-02. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, 

La Jolla, CA 92037. 

Chivers, S. NMFS, Southwest Fisheries Science Center, 8604 La Jolla Shores Drive, La Jolla, CA 92037. Ferguson, 

M. C. and J. Barlow. 2003. Addendum: Spatial distribution and density of cetaceans in the eastern tropical 

Pacific Ocean based on summer/fall research vessel surveys in 1986-96. Administrative Report LJ-01-04 

(addendum), Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores 

Drive, La Jolla, CA 92037. 

Chivers, S. J., R. W. Baird, D. J. McSweeney, D. L. Webster, N. M. Hedrick, and J. C. Salinas. 2007. Genetic 

variation and evidence for population structure in eastern North Pacific false killer whales (Pseudorca 

crassidens). Can. J. Zool. 85: 783-794. 

Forney, K.A. and D. R. Kobayashi. In press. Updated estimates of mortality and injury of cetaceans in the Hawaiibased longline fisheries, 1994-2005. NOAA Tech Memo NMFS-SWFSC-xxx. 

Kobayashi, D. R. and K. E. Kawamoto. 1995. Evaluation of shark, dolphin, and monk seal interactions with 

Northwestern Hawaiian Island bottom-fishing activity: a comparison of two time periods and an estimate of 

economic impacts. Fisheries Research 23: 11-22. 

Maldini, D., L. Mazzuca, and S. Atkinson. 2005. Odontocete stranding patterns in the Main Hawaiian Islands 

237
(1937-2002): How do they compare with live animal surveys? Pacific Science 59(1):55-67. 

Miyashita, T. 1993. Abundance of dolphin stocks in the western North Pacific taken by the Japanese drive fishery. 

Rep. Int. Whal. Commn. 43:417-437. 

Mobley, J.R. , Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and 

abundance of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. 

Rep. LJ-00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 26 pp. 

Mobley, J.R. 2001. Results of 2001 aerial surveys north of Kauai. Report to North Pacific Acoustic Laboratory 

program. 20 pp. Available as downloadable pdf file at: 

http://socrates.uhwo.hawaii.edu/SocialSci/jmobley/2001NPAL.pdf 

Mobley, J.R. 2002. Results of 2002 aerial surveys north of Kauai. Report to North Pacific Acoustics Laboratory 

program. 20 pp. Available as downloadable pdf file at: 

http://socrates.uhwo.hawaii.edu/SocialSci/jmobley/2002NPAL.pdf 

Mobley, J.R. 2003. Results of 2003 aerial surveys north of Kauai. Report to North Pacific Acoustics Laboratory 

program. 20 pp. Available as downloadable pdf file at: 

http://socrates.uhwo.hawaii.edu/SocialSci/jmobley/2003NPAL.pdf 

Mobley, J.R. 2004. Results of 2004 aerial surveys north of Kauai. Report to North Pacific Acoustics Laboratory 

program. 25 pp. Available as downloadable pdf file at: 

http://socrates.uhwo.hawaii.edu/SocialSci/jmobley/2004NPAL.pdf 

Nitta, E. 1991. The marine mammal stranding network for Hawaii: an overview. In: J.E. Reynolds III, D.K. Odell 

(eds.), Marine Mammal Strandings in the United States, pp.56-62. NOAA Tech. Rep. NMFS 98, 157 pp. 

Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

NMFS, Pacific Islands Region, Observer Program, 1602 Kapiolani Blvd, Suite 1110, Honolulu, HI 96814. 

NMFS, Southwest Fisheries Science Center, 8604 La Jolla Shores Drive, La Jolla, CA 92027. 

NMFS Western Pacific Pelagic Fisheries Biological Opinion 2001. Available from Pacific Islands Region, 1602 

Kapiolani Blvd, Suite 1110, Honolulu, HI 96814 (http://swr.nmfs.noaa.gov/pir). 

Norris, K. S., B. Würsig, R. S. Wells, and M. Würsig. 1994. The Hawaiian Spinner Dolphin. University of 

California Press, 408 pp. 

Norris, K. S. and T. P. Dohl. 1980. Behavior of the Hawaiian spinner dolphin, Stenella longirostris. Fish. Bull.

77:821-849. 

Perrin, W.F., G. P. Donovan and J. Barlow. 1994. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Special Issue 

15, 629 pp. 

Shallenberger, E.W. 1981. The status of Hawaiian cetaceans. Final report to U.S. Marine Mammal Commission. 

MMC-77/23, 79pp. 

Stacey, P. J., S. Leatherwood, and R. W. Baird. 1994. Pseudorca crassidens. Mamm. Spec. 456:1-6. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp.

Wade, P. R. and T. Gerrodette. 1993. Estimates of cetacean abundance and distribution in the eastern tropical 

Pacific. Rep. Int. Whal. Commn. 43:477-493. 

238
Revised 03/15/2005

KILLER WHALE (Orcinus orca): Hawaiian Stock

STOCK DEFINITION AND GEOGRAPHIC RANGE

 Killer whales have been 

observed in all oceans and seas of the 

world (Leatherwood and Dahlheim 

1978). Although reported from tropical 

and offshore waters (Heyning and 

Dahlheim 1988), killer whales prefer the 

colder waters of both hemispheres, with 

greatest abundances found within 800 

km of major continents (Mitchell 1975). 

They are considered rare in Hawaiian 

waters. No killer whales were seen 

during 1993-98 aerial surveys within 

about 25 nmi of the main Hawaiian 

Islands, but one sighting was reported 

during subsequent surveys (Mobley et al. 

2000, 2001). Two sightings of killer 

whales were made during a 2002 

shipboard survey of waters within the 

U.S. Exclusive Economic Zone (EEZ) of 

the Hawaiian Islands (Figure 1; Barlow 

2003). One stranding from the island of 

Hawaii was reported in 1950 (Richards 

1952) and another in 2004 (R.W. Baird, 

pers. comm.). Except in the northeastern 

Pacific where "resident", "transient", 

and “offshore” stocks have been 

described for coastal waters of Alaska, British Columbia, and Washington to California (Bigg 1982; Leatherwood et 

al. 1990, Bigg et al. 1990, Ford et al. 1994), little is known about stock structure of killer whales in the North 

Pacific. Baird et al. (2003) report a sighting of this species off the island of Hawaii in 2003, and also note analyses 

of genetic results from one sample collected, indicating a haplotype similar to the Gulf of Alaska “transient” killer 

whales. For the Marine Mammal Protection Act (MMPA) stock assessment reports, five killer whale stocks are 

recognized within the Pacific U.S. EEZ 1) the Eastern North Pacific Northern Resident stock - occurring from 

British Columbia through Alaska, 2) the Eastern North Pacific Southern Resident stock - occurring within the inland 

waters of Washington State and southern British Columbia, 3) the Eastern North Pacific Transient stock - occurring 

from Alaska through California, 4) the Eastern North Pacific Offshore stock - occurring from Southeast Alaska 

through California, and 5) the Hawaiian stock (this report). Stock Assessment Reports for the Eastern North 

Pacific Northern Resident stock and the Eastern North Pacific Transient stocks can be found in the Alaska Region 

stock assessment reports; all other killer whale stock assessments are included in the Pacific Region stock 

assessments. 

POPULATION SIZE

 Population sizes for killer whales in the coastal waters of British Columbia and Washington are known 

from photo-identification studies (Bigg et al. 1990). The population of killer whales in the eastern tropical Pacific 

has been estimated from shipboard sightings surveys (Wade and Gerrodette 1993). As part of the Marine Mammal 

Research Program of the Acoustic Thermometry of Ocean Climate (ATOC) study, a total of twelve aerial surveys 

were conducted within about 25 nmi of the main Hawaiian Islands in 1993, 1995 and 1998 (Mobley et al. 2000), but 

no sightings of killer whales were made. A 2002 shipboard line-transect survey of the entire Hawaiian Islands EEZ 

resulted in an abundance estimate of 430 (CV=0.72) killer whales (Barlow 2003). This is currently the best 

available abundance estimate for this stock. 

Minimum Population Estimate

 The log-normal 20th percentile of the 2002 abundance estimate is 250 killer whales. 

W180 W175 W170 W165 W160 W155 W150

N10

N15

N20

N25

N30

N35

Figure 1. Killer whale sighting locations during the 2002 shipboard 

survey of U.S. EEZ waters surrounding the Hawaiian Islands 

(Barlow 2003; see Appendix 2 for details on timing and location of 

survey effort). Outer line represents approximate boundary of survey 

area and U.S. EEZ. 

239
Current Population Trend

 No data are available on current population trend. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No data are available on current and maximum net productivity rate in Hawaiian waters. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size 

(250) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.50 

(for a stock of unknown status with no known fishery mortality or serious injury within the Hawaiian Islands EEZ; 

Wade and Angliss 1997), resulting in a PBR of 2.5 killer whales per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

 Information on fishery-related mortality and serious injury of cetaceans in Hawaiian waters is limited, but 

the gear types used in Hawaiian fisheries are responsible for marine mammal mortality and serious injury in other 

fisheries throughout U.S. waters. Gillnets appear to capture marine mammals wherever they are used, and float lines 

from lobster traps and longlines can be expected to occasionally entangle whales (Perrin et al. 1994). 

 Interactions with cetaceans have been reported for all Hawaiian pelagic fisheries (Nitta and Henderson 

1993), but killer whale interactions appear to be rare. In 1990, a solitary killer whale was reported to have removed 

the catch from a longline in Hawaii (Dollar 1991). None were observed hooked or entangled in the Hawaii-based 

longline fishery between 1994 and 2002, with approximately 4-25% of all effort observed (Forney 2004). Interaction 

rates between dolphins and the NWHI bottomfish fishery have been estimated based on studies conducted in 1990-

1993, indicating that an average of 2.67 dolphin interactions, most likely involving bottlenose and rough-toothed 

dolphins, occurred for every 1000 fish brought on board (Kobayashi and Kawamoto 1995). Fishermen claim 

interactions with dolphins that steal bait and catch are increasing. It is not known whether these interactions result 

in serious injury or mortality of dolphins, nor whether killer whales are involved. 

STATUS OF STOCK

 The status of killer whales in Hawaiian waters relative to OSP is unknown, and there are insufficient data to 

evaluate trends in abundance. No habitat issues are known to be of concern for this species. This species is not 

listed as “threatened” or “endangered” under the Endangered Species Act (1973), nor as “depleted” under the 

MMPA. The Hawaiian stock of killer whales is not considered strategic under the 1994 amendments to the MMPA 

given the absence of reported fisheries related mortality or serious injury. Insufficient information is available to 

determine whether the total fishery mortality and serious injury for killer whales is insignificant and approaching 

zero mortality and serious injury rate. 

REFERENCES 

Baird, R.W., D.J. McSweeney, D.L. Webster, A.M. Gorgone and A.D. Ligon. 2003. Studies of odontocete 

population structure in Hawaiian waters: results of a survey through the main Hawaiian Islands in May and 

June 2003. Report prepared under Contract No. AB133F-02-CN-0106 from the National Oceanic and 

Atmospheric Administration, Western Administrative Support Center, 7600 Sand Point Way N.E., Seattle, 

WA 98115 USA.

Barlow, J. 2003. Cetacean abundance in Hawaiian waters during summer/fall 2002. Admin. Rep. LJ-03-13. 

Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La 

Jolla, CA 92037. 

Bigg, M. A. 1982. An assessment of killer whale (Orcinus orca) stocks off Vancouver Island, British Columbia. 

Rep. Int. Whal. Commn. 32:655-666. 

Bigg, M. A., P. F. Olesiuk, G. M. Ellis, J. K. B. Ford, and K. C. Balcomb, III. 1990. Social organization and 

genealogy of resident killer whales (Orcinus orca) in the coastal waters of British Columbia and 

Washington State. Rep. Int. Whal. Commn. (Spec. Iss. 12):383-405. 

Dollar, R. A. 1991. Summary of swordfish longline observations in Hawaii, July 1990-March 1991. Southwest 

Fish. Cent. Admin. Rep. H-91-09, 13 pp. 

Ford, J. K. B., G. M. Ellis, and K.C. Balcomb. 1994. Killer whales. The natural history and genealogy of Orcinus 

orca in British Columbia and Washington State. UBC Press, Vancouver, Canada. 

240
Forney, K.A. 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994-2002. 

Admin. Rep. LJ-04-07. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92037. 17 pp. 

Kobayashi, D. R. and K. E. Kawamoto. 1995. Evaluation of shark, dolphin, and monk seal interactions with 

Northwestern Hawaiian Island bottomfishing activity: a comparison of two time periods and an estimate of 

economic impacts. Fisheries Research 23: 11-22. 

Leatherwood, J. S., and M. E. Dahlheim. 1978. Worldwide distribution of pilot whales and killer whales. Naval 

Ocean Systems Center, Tech. Rep. 443:1-39. 

Heyning, J. E. and M. E. Dahlheim. 1988. Orcinus orca. Mamm. Spec.304:1-9. 

Leatherwood, S., C. O. Matkin, J. D. Hall, and G. M. Ellis. 1990. Killer whales, Orcinus orca, photo-identified in 

Prince William Sound, Alaska, 1976 through 1987. Can Field-Nat. 104:362-371. 

Mitchell, E. D. 1975. Report on the meeting on small cetaceans, Montreal, April 1-11, 1974. J. Fish. Res. Board 

Canada, 32:914-916. 

Mobley, J. R., Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and 

abundance of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. 

Rep. LJ-00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 26 pp. 

Mobley, J. R. , L. Mazzuca, A. S. Craig, M. W. Newcomer, and S. S. Spitz. 2001. Killer whales (Orcinus orca) 

sighted West of Ni'ihau, Hawai'i. Pacific Science 55:301_303. 

Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

Perrin, W.F., G. P. Donovan and J. Barlow. 1994. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Special Issue 

15, 629 pp. 

Richards, L. P. 1952. Cuvier's beaked whale from Hawaii. J. Mamm. 33:255. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

Wade, P. R. and T. Gerrodette. 1993. Estimates of cetacean abundance and distribution in the eastern tropical 

Pacific. Rep. Int. Whal. Commn. 43:477-493. 

241
Revised 12/15/2006

SHORT-FINNED PILOT WHALE (Globicephala macrorhynchus): 

Hawaiian Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE 

 Short-finned pilot whales are found in all 

oceans, primarily in tropical and warm-temperate 

waters. They are commonly observed around the 

main Hawaiian Islands and are also present around 

the Northwestern Hawaiian Islands (Shallenberger 

1981; Barlow 2006). During a 2002 shipboard 

survey of waters within the U.S. Exclusive 

Economic Zone (EEZ) of the Hawaiian Islands, 25 

sightings of short-finned pilot whales were made 

(Figure 1; Barlow 2006). Fourteen strandings of 

short-finned pilot whales have been documented 

from the main Hawaiian Islands, including five 

mass strandings (Tomich 1986; Nitta 1991; 

Maldini 2003). Stock structure of short-finned 

pilot whales has not been adequately studied in the 

North Pacific, except in Japanese waters, where 

two stocks have been identified based on 

pigmentation patterns and differences in the 

shape of the heads of adult males (Kasuya et al. 

1988). The pilot whales in Hawaiian waters are 

similar morphologically to the Japanese 

"southern form." Preliminary photoidentification work with pilot whales in Hawaii indicated a high degree of site fidelity around the main island of 

Hawaii (Shane and McSweeney 1990) and around Kauai and Niihau (Baird et al. 2006). 

 Genetic analyses of tissue samples collected near the main Hawaiian Islands indicate that Hawaiian shortfinned pilot whales are reproductively isolated from short-finned pilot whales found in the eastern Pacific Ocean (S. 

Chivers, NMFS/SWFSC, unpublished data); however, the offshore range of this Hawaiian population is unknown. 

Fishery interactions with short-finned pilot whales demonstrate that this species also occurs in U.S. EEZ waters of 

Palmyra Atoll and Johnston Atoll (Figure 2), but it is not known whether these animals are part of the Hawaiian 

stock or whether they represent separate stocks of short-finned pilot whales. Based on patterns of movement and 

population structure observed in other island-associated cetaceans (Norris and Dohl 1980; Norris et al.1994; Baird et 

al. 2001, 2003; S. Chivers, pers. comm.), it is possible that the animals around Palmyra Atoll and Johnston Atoll are 

one or more separate stocks. Efforts are currently underway to obtain additional samples of short-finned pilot 

whales for further studies of population structure in the North Pacific Ocean. For the Marine Mammal Protection 

Act (MMPA) stock assessment reports, short-finned pilot whales within the Pacific U.S. EEZ are divided into two 

discrete, non-contiguous areas: 1) Hawaiian waters (this report), and 2) waters off California, Oregon and 

Washington. Information on short-finned pilot whales around Palmyra Atoll and Johnston Atoll will provisionally 

be included with this stock assessment report, recognizing that separate stock status may be warranted for these 

animals in the future. Estimates of abundance, potential biological removals, and status determinations will be 

presented separately for U.S. waters of the Hawaiian Islands, Palmyra Atoll, and Johnston Atoll. 

POPULATION SIZE

 Estimates of short-finned pilot whale populations have been made off Japan (Miyashita 1993) and in the 

eastern tropical Pacific (Wade and Gerrodette 1993), but it is not known whether any of these animals are part of the 

same population that occurs around the Hawaiian Islands. As part of the Marine Mammal Research Program of the 

Acoustic Thermometry of Ocean Climate (ATOC) study, a total of twelve aerial surveys were conducted within 

about 25 nmi of the main Hawaiian Islands in 1993, 1995 and 1998. An abundance estimate of 1,708 (CV=0.32) 

short-finned pilot whales was calculated from the combined survey data (Mobley et al. 2000). This study 

underestimated the total number of short-finned pilot whales within the U.S. EEZ off Hawaii, because areas around 

the Northwestern Hawaiian Islands (NWHI) and beyond 25 nautical miles from the main islands were not surveyed. 

Figure 1. Short-finned pilot whale sighting locations during 

the 2002 shipboard survey of U.S. EEZ waters surrounding the 

Hawaiian Islands (Barlow 2006); see Appendix 2 for details on 

timing and location of survey effort). Outer line represents 

approximate boundary of survey area and U.S. EEZ. 

W180 W175 W170 W165 W160 W155 W150

N10

N15

N20

N25

N30

N35

242
Furthermore, the data on which this estimate was based are now over 5 years old. A 2002 shipboard line-transect 

survey of the entire Hawaiian Islands EEZ resulted in an abundance estimate of 8,846 (CV=0.49) short-finned pilot 

whales (Barlow 2006). This is currently the best available abundance estimate for short-finned pilot whales within 

the Hawaiian Islands EEZ. 

No abundance estimates are currently available for short-finned pilot whales in U.S. EEZ waters of 

Palmyra Atoll; however, density estimates for short-finned pilot whales in other Pacific regions can provide a range 

of likely abundance estimates in this unsurveyed region. Published estimates of short-finned pilot whale density 

(animals per km2

) in the Pacific are: 0.0040 (CV=0.38) for the U.S. EEZ of the Hawaiian Islands (Barlow 2006); 

0.0237 (CV=0.32) for nearshore waters surrounding the main Hawaiian Islands (Mobley et al. 2000), 0.0084 

(CV=0.14) and 0.0040 (CV=0.23) for the eastern tropical Pacific Ocean (Wade and Gerrodette 1993; Ferguson and 

Barlow 2003), and 0.0025 (CV=0.29) for the eastern tropical Pacific Ocean west of 120°W and north of 5°N 

(Ferguson and Barlow 2003). Applying the lowest and highest of these density estimates to U.S. EEZ waters 

surrounding Palmyra Atoll (area size = 352,821 km2

) yields a range of plausible abundance estimates of 891-8,362 

short-finned pilot whales. Similarly, there are no abundance estimates for short-finned pilot whales in U.S. EEZ 

waters of Johnston Atoll. Applying the lowest and highest of the above density estimates to U.S. EEZ waters 

surrounding Johnston Atoll (area size = 443,586 km2

) yields a range of plausible abundance estimates of 1,121-

10,513 short-finned pilot whales. 

 

Minimum Population Estimate

 The log-normal 20th percentile of the 2002 abundance estimate for the Hawaiian Islands EEZ (Barlow 

2006) is 6,511 short-finned pilot whales. No minimum population estimate is currently available for waters 

surrounding Palmyra Atoll or Johnston Atoll, but the short-finned pilot whale density estimates from other Pacific 

regions (Barlow 2006, Mobley et al. 2000, Wade and Gerrodette 1993, Ferguson and Barlow 2003; see above) can 

provide a range of likely values. The lognormal 20th percentiles of plausible abundance estimates for the Palmyra 

Atoll EEZ, based on the densities observed elsewhere, range from 701 to 6,429 short-finned pilot whales. The 

lognormal 20th percentiles of plausible abundance estimates for the Johnston Atoll EEZ, based on the densities 

observed elsewhere, range from 882 to 8,083 short-finned pilot whales. 

Current Population Trend

 No data are available on current population trend. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No data are available on current or maximum net productivity rate. 

POTENTIAL BIOLOGICAL REMOVAL 

 The potential biological removal (PBR) level for the Hawaiian short-finned pilot whale stock is calculated 

as the minimum population size (6,511) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) 

times a recovery factor of 0.50 (for a species of unknown status with no known fishery mortality and serious injury 

within the U.S. EEZ of the Hawaiian Islands; Wade and Angliss 1997), resulting in a PBR of 65 short-finned pilot 

whales per year. No separate PBR can presently be calculated for Palmyra Atoll waters, but based on the range of 

plausible minimum abundance estimates (701-6,429), a recovery factor of 0.50 (for a species of unknown status with 

no known fishery mortality and serious injury within the Palmyra Atoll EEZ; Wade and Angliss 1997), and the 

default growth rate (1⁄2 of 4%), the PBR would likely fall between 7.0 and 64 short-finned pilot whales per year. 

Similarly, based on the range of plausible minimum abundance estimates for Johnston Atoll (882-8,083), a recovery 

factor of 0.40 (for a species of unknown status with a fishery mortality and serious injury rate CV>0.80 within the 

Johnston Atoll EEZ; Wade and Angliss 1997), and the default growth rate (1⁄2 of 4%), the PBR would likely fall 

between 7.1 and 65 short-finned pilot whales per year. 

 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

Information on fishery-related mortality of cetaceans in Hawaiian waters is limited, but the gear types used 

in Hawaiian fisheries are responsible for marine mammal mortality and serious injury in other fisheries throughout 

U.S. waters. Gillnets appear to capture marine mammals wherever they are used, and float lines from lobster traps 

and longlines can be expected to occasionally entangle whales (Perrin et al. 1994). 

243
 Interactions with cetaceans have been reported for all Hawaiian pelagic fisheries (Nitta and Henderson 

1993). Between 1994 and 2004, six short-finned pilot whales were observed hooked in the Hawaii-based longline 

fishery with approximately 4-26% of all effort observed (Table 1; Forney and Kobayashi 2005). During the 

observed 18,353 sets, the average interaction rate of short-finned pilot whales was 0.33 short-finned pilot whales per 

1000 sets. Two of the animals caught were dead upon gear retrieval, two were considered seriously injured, and one 

taken near Palmyra Atoll was considered not seriously injured (Forney and Kobayashi 2005), based on an evaluation 

of the observer’s description of the interaction and 

following established guidelines for assessing 

serious injury in marine mammals (Angliss and 

DeMaster 1998). Average 5-yr estimates of annual 

mortality and serious injury for 2000-2004 are 3.6 

(CV = 0.69) short-finned pilot whales outside of the 

U.S. EEZs, and 0.6 (CV = 1.00) within the U.S. 

EEZ of Johnston Atoll (Table 1). No short-finned 

pilot whales were observed killed or seriously 

injured within the Hawaiian Islands EEZ or the 

Palmyra Atoll EEZ during 2000-2004. Ten 

additional unidentified cetaceans, which may have 

been short-finned pilot whales, were also taken in 

this fishery. Two of these unidentified cetaceans 

were within the EEZ of Palmyra Atoll, and three 

were in the EEZ of the Hawaiian Islands (Figure 2, 

Forney and Kobayashi 2005). Since 2001, the 

Hawaii-based longline fishery has undergone a 

series of regulatory changes, primarily to protect sea 

turtles (NMFS 2001). Potential impacts of these 

regulatory changes on the rate of short-finned pilot 

whale interactions are unknown. 

 Interaction rates between dolphins and the 

NWHI bottomfish fishery have been estimated 

based on studies conducted in 1990-1993, indicating 

that an average of 2.67 dolphin interactions, most 

likely involving bottlenose and rough-toothed 

dolphins, occurred for every 1000 fish brought on board (Kobayashi and Kawamoto 1995). Fishermen claim 

interactions with dolphins that steal bait and catch are increasing. It is not known whether these interactions result 

in serious injury or mortality of dolphins, nor whether short-finned pilot whales are involved. 

Table 1. Summary of available information on incidental mortality and serious injury of short-finned pilot whales 

(Hawaiian stock) in commercial fisheries, within and outside of the U.S. EEZs (Forney and Kobayashi 2005). Mean 

annual takes are based on 2000-2004 data unless otherwise indicated. 

Observed and estimated mortality and serious injury of short-finned pilot whales, by EEZ region 

Outside of U.S. EEZs Hawaiian Islands EEZ Johnston Atoll EEZ 

Fishery 

Name Year Data Type 

Percent 

Observer 

Coverage 

Obs. Estimated 

(CV) 

Mean 

Annual 

Takes 

(CV) 

Obs. Estimated 

(CV) 

Mean 

Annual 

Takes 

(CV) 

Obs. Estimated 

(CV) 

Mean 

Annual 

Takes 

(CV) 

Hawaiibased 

longline 

fishery 

2000 

2001 

2002 

2003 

2004 

observer 

data 

11.8% 

22.7% 

24.9% 

21.9% 

25.7% 

2 

1 

0 

0 

0 

13 (0.88) 

5 (1.00) 

0 (-) 

0 (-) 

0 (-) 

3.6 

(0.69) 

0 

0 

0 

0 

0 

0 (-) 

0 (-) 

0 (-) 

0 (-) 

0 (-) 

0 (-) 

0 

0 

0 

0 

1 

0 (-) 

 0 (-) 

0 (-) 

0 (-) 

3 (1.00) 

0.6 

(1.00) 

Minimum total annual takes within U.S. EEZ waters 0.6 (1.00) 

STATUS OF STOCK

 The status of short-finned pilot whales in Hawaiian waters relative to OSP is unknown, and there are 

insufficient data to evaluate trends in abundance. No habitat issues are known to be of concern for this species. 

They are not listed as “threatened” or “endangered” under the Endangered Species Act (1973), nor as “depleted” 

Figure 2. Locations of short-finned pilot whale takes (filled 

diamonds) and possible takes of this species (open diamonds) 

in the Hawaii-based longline fishery, 1994-2002. Solid lines 

represent the U. S. EEZ. Set locations in this fishery are 

summarized in Appendix 1. 

244
under the MMPA. The Hawaiian stock of short-finned pilot whales is not considered strategic under the 1994 

amendments to the MMPA, because the estimated rate of mortality and serious injury within the Hawaiian Islands 

EEZ is zero. However, potential effect of mortality in the Hawaii-based fishery in international waters is not known. 

Although no estimates of abundance or PBR are currently available for short-finned pilot whales around Johnston 

Atoll, the estimated average rate of mortality and serious injury of short-finned pilot whales within the EEZ of 

Johnston Atoll (0.6 animals per year) is below the range of likely PBRs (7.1 to 65) for this region. There have been 

no serious injuries or mortalities of short-finned pilot whales within the Palmyra Atoll EEZ. Insufficient 

information is available to determine whether the total fishery mortality and serious injury for short-finned pilot 

whales is insignificant and approaching zero mortality and serious injury rate. 

REFERENCES 

Angliss, R. P. and D. P. DeMaster. 1998. Differentiating Serious and Non-Serious Injury of Marine Mammals 

Taken Incidental to Commercial Fishing Operations: Report of the Serious Injury Workshop 1-2 April 

1997, Silver Spring, Maryland. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR-13. 48 pp.

Baird, R. W., Ligon, A. D., Hooker, S. K., and A. M. Gorgone. 2001. Subsurface and nighttime behaviour of 

pantropical spotted dolphins in Hawai’i. Can. J. Zool. 79:988-996. 

Baird, R.W., D.J. McSweeney, D.L. Webster, A.M. Gorgone, and A.D. Ligon. 2003. Studies of odontocete 

population structure in Hawaiian waters: Results of a survey through the main Hawaiian Islands in May 

and June 2003. Report prepared under contract #AB133F-02-CN-0106 to the Southwest Fisheries Science 

Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 92037, USA. 10p. 

Baird, R.W., G.S. Schorr, D.L. Webster, S.D. Mahaffy, A.B. Douglas, A.M. Gorgone, and D.J. McSweeney. 2006. 

A survey for odontocete cetaceans off Kaua'i and Ni'ihau, Hawai'i, during October and November 2005: 

evidence for population structure and site fidelity. Report prepared under contract #AB133F05SE519 to 

Pacific Islands Fisheries Science Center, National Marine Fisheries Service, 2570 Dole Street, Honolulu, 

HI 96822, USA. 16p. 

Barlow, J. 2006. Cetacean abundance in Hawaiian waters estimated from a summer/fall survey in 2002. Marine 

Mammal Science 22: 446–464. 

Chivers, S. NMFS, Southwest Fisheries Science Center, 8604 La Jolla Shores Drive, La Jolla, CA 92037. 

Ferguson, M. C. and J. Barlow. 2003. Addendum: Spatial distribution and density of cetaceans in the eastern 

tropical Pacific Ocean based on summer/fall research vessel surveys in 1986-96. Administrative Report LJ01-04 (addendum), Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla 

Shores Drive, La Jolla, CA 92037. 

Forney, K.A. and D. Kobayashi. 2005. Updated estimates of mortality and injury of cetaceans in the Hawaii-based 

longline fishery, 1994-2004. Draft report. Document PSRG-07 presented to the Pacific Scientific Review 

Group, November 16-17, 2005. Available from Southwest Fisheries Science Center, National Marine 

Fisheries Service, 8604 La Jolla Shores Drive, La Jolla, CA 92037. 

Kasuya, T., T. Miyashita, and F. Kasamatsu. 1988. Segregation of two forms of short-finned pilot whales off the 

Pacific coast of Japan. Sci. Rep. Whales Res. Inst. 39:77-90. 

Kobayashi, D. R. and K. E. Kawamoto. 1995. Evaluation of shark, dolphin, and monk seal interactions with 

Northwestern Hawaiian Island bottomfishing activity: a comparison of two time periods and an estimate of 

economic impacts. Fisheries Research 23: 11-22. 

Maldini, D. 2003. Abundance and distribution patterns of Hawaiian odontocetes: focus on O’ahu. Doctoral 

dissertation, University of Hawai’i at Manoa. 122p. 

Miyashita, T. 1993. Abundance of dolphin stocks in the western North Pacific taken by the Japanese drive fishery. 

Rep. Int. Whal. Commn. 43:417-437. 

Mobley, J. R. , Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and 

abundance of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. 

Rep. LJ-00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 26 pp. 

Nitta, E. 1991. The marine mammal stranding network for Hawaii: an overview. In: J.E. Reynolds III, D.K. Odell 

(eds.), Marine Mammal Strandings in the United States, pp.56-62. NOAA Tech. Rep. NMFS 98, 157 pp. 

Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

NMFS, Southwest Fisheries Science Center, 8604 La Jolla Shores Drive, La Jolla, CA 92037. 

NMFS 2001. Western Pacific Pelagic Fisheries Biological Opinion. Available from Pacific Islands Region, 1602 

Kapiolani Blvd, Suite 1110, Honolulu, HI 96814 (http://swr.nmfs.noaa.gov/pir). 

245
Norris, K. S., B. Würsig, R. S. Wells, and M. Würsig. 1994. The Hawaiian Spinner Dolphin. University of 

California Press, 408 pp. 

Norris, K. S. and T. P. Dohl. 1980. Behavior of the Hawaiian spinner dolphin, Stenella longirostris. Fish. Bull.

77:821-849. 

Perrin, W.F., G. P. Donovan and J. Barlow. 1994. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Special Issue 

15, 629 pp. 

Shallenberger, E.W. 1981. The status of Hawaiian cetaceans. Final report to U.S. Marine Mammal Commission. 

MMC-77/23, 79pp. 

Shane, S. H. and D. McSweeney. 1990. Using photo-identification to study pilot whales social organization. Rep. 

Int. Whal. Commn. (Spec. Iss. 12):259-263. 

Tomich, P. Q. 1986. Mammals in Hawaii: A Synopsis and Notational Bibliography. Bishop Museum Press, Hawaii, 

375 pp. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

Workshop April 3-5, 1996, Seattle, WA. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR-12. 93 

pp. 

Wade, P. R. and T. Gerrodette. 1993. Estimates of cetacean abundance and distribution in the eastern tropical 

Pacific. Rep. Int. Whal. Commn. 43:477-493.

246
Revised 03/15/2005

BLAINVILLE'S BEAKED WHALE (Mesoplodon densirostris): 

Hawaiian Stock

STOCK DEFINITION AND GEOGRAPHIC RANGE

 Blainville's beaked whale has a 

cosmopolitan distribution in tropical and 

temperate waters, apparently the most 

extensive known distribution of any 

Mesoplodon species (Mead 1989). Two 

strandings were reported in 1961 from 

Midway Island (Galbreath 1963) and 

another in 1983 from Laysan Island 

(Nitta 1991). Sixteen sightings were 

reported from the main islands by 

Shallenberger (1981), who suggested 

that Blainville's beaked whales were 

present off the Waianae Coast of Oahu 

for prolonged periods annually. Three 

sightings were made during a 2002 

shipboard survey of waters within the 

U.S. Exclusive Economic Zone (EEZ) of 

the Hawaiian Islands (Figure 1; Barlow 

2003). While nothing is known about 

stock structure, some genetic samples 

have been collected recently from 

around the main Hawaiian islands, and 

there have been re-sightings of 

individuals from the island of Hawaii 

(R.W. Baird, pers. comm.). For the 

Marine Mammal Protection Act 

(MMPA) stock assessment reports, three 

Mesoplodon stocks are defined within the Pacific U.S. EEZ : 1) M. densirostris in Hawaiian waters (this report), 2) 

M. stejnegeri in Alaskan waters, and 3) all Mesoplodon species off California, Oregon and Washington. 

POPULATION SIZE

 As part of the Marine Mammal Research Program of the Acoustic Thermometry of Ocean Climate (ATOC) 

study, a total of twelve aerial surveys were conducted within about 25 nmi of the main Hawaiian Islands in 1993, 

1995 and 1998. Seven sightings of Blainville’s beaked whales were made. An abundance estimate of 68 (CV=0.60) 

Blainville’s beaked whales was calculated from the combined survey data (Mobley et al. 2000). This study 

underestimated the total number of Blainville’s beaked whales within the U.S. EEZ off Hawaii, because areas 

around the Northwestern Hawaiian Islands (NWHI) and beyond 25 nautical miles from the main islands were not 

surveyed. Furthermore, this species is known to spend a large proportion of time diving, causing additional 

downward bias in the abundance estimate. The data on which this estimate was based are now over 5 years old. A 

2002 shipboard line-transect survey of the entire Hawaiian Islands EEZ resulted in an abundance estimate of 2,138 

(CV=0.77) Blainville’s beaked whales (Barlow 2003), including a correction factor for missed diving animals. This 

is currently the best available abundance estimate for this stock. 

Minimum Population Estimate

 The log-normal 20th percentile of the 2002 abundance estimate is 1,204 Blainville’s beaked whales. . 

 

Current Population Trend

 No data are available on current population trend. 

W180 W175 W170 W165 W160 W155 W150

N10

N15

N20

N25

N30

N35

Figure 1. Sighting locations of Mesoplodon densirostris (filled 

circles), Indopacetus pacificus (triangle), and unidentified 

Mesoplodon beaked whales (cross) during the 2002 shipboard 

cetacean survey of U.S. EEZ waters surrounding the Hawaiian 

Islands (Barlow 2003; see Appendix 2 for details on timing and 

location of survey effort). Outer line indicates approximate boundary 

of survey area and U.S. EEZ.

247
CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No data are available on current or maximum net productivity rate. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size 

(1,204 ) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.40 

(for a species of unknown status with a Hawaiian Islands EEZ fishery mortality and serious injury rate CV>0.80; 

Wade and Angliss 1997), resulting in a PBR of 9.6 Blainville’s beaked whales per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

 Information on fishery-related 

mortality of cetaceans in Hawaiian 

waters is limited, but the gear types used 

in Hawaiian fisheries are responsible for 

marine mammal mortality and serious 

injury in other fisheries throughout U.S. 

waters. Gillnets appear to capture marine 

mammals wherever they are used, and 

float lines from lobster traps and 

longlines can be expected to occasionally 

entangle whales (Perrin et al. 1994). 

 Interactions with cetaceans are 

reported for all pelagic fisheries (Nitta 

and Henderson 1993). Between 1994 and 

2002, one Blainville’s beaked whale was 

observed hooked and killed in the 

Hawaii-based longline fishery, with 

approximately 4-25% of all effort 

observed (Table 1; Forney 2004). Three 

additional unidentified cetaceans, which 

may have been Blainville’s beaked 

whales, were also taken in this fishery 

(Figure 2, Forney 2004). During the 905 

observed trips with 11,014 sets, the 

average interaction rate of Blainville’s 

beaked whales was one animal per 905 

fishing trips, or one animal per 11,014 

sets. Average 5-yr estimates of annual 

mortality and serious injury for 1998-

2002 are zero Blainville’s beaked whales outside of the U.S. EEZs, and 0.8 (CV = 1.00) within the Hawaiian Islands 

EEZ (Table 1). Since 2001, the Hawaii-based longline fishery has undergone a series of regulatory changes, 

primarily to protect sea turtles (NMFS 2001). Potential impacts of these regulatory changes on the rate of 

Blainville’s beaked whale interactions are unknown. 

Other Mortality

 In recent years, there has been increasing concern that loud underwater sounds, such as active sonar and 

seismic operations, may be harmful to beaked whales (Malakoff 2002). The use of active sonar from military vessels 

has been implicated in mass strandings of beaked whales in the Mediterranean Sea during 1996 (Frantzis 1998), the 

Bahamas during 2000 (U.S. Dept. of Commerce and Secretary of the Navy 2001), and the Canary Islands 2002 

(Martel 2002). Similar military active sonar operations occur around the Hawaiian islands. No estimates of 

potential mortality or serious injury are available for U.S. waters. 

 

Figure 2. Location of the single Blainville’s beaked whale take 

(filled diamond) and possible takes of this species (open diamonds) 

in the Hawaii-based longline fishery, 1994-2002. Solid lines 

represent the U.S. EEZ. 

248
Table 1. Summary of available information on incidental mortality and serious injury of Blainville’s beaked whales 

(Hawaiian stock) in commercial fisheries, within and outside of the Hawaiian Islands EEZ (Forney 2004). Mean 

annual takes are based on 1998-2002 data unless otherwise indicated. 

Mortality and Serious Injury 

outside of U.S. EEZ

Mortality and Serious Injury 

within Hawaiian Islands EEZ

Fishery Name Year Data Type

Percent 

Observer 

Coverage

Observed Estimated 

(CV)

Mean Annual 

Takes 

(CV)

Observed Estimated 

(CV)

Mean Annual 

Takes 

(CV)

Hawaii-based 

longline fishery 

1998 

1999 

2000 

2001 

2002

1998-2002 

observer 

data

4.6% 

3.5% 

11.8% 

22.7% 

24.9%

0 

0 

0 

0 

0

0 (-) 

0 (-) 

0 (-) 

0 (-) 

0 (-)

0 (-)

0 

0 

0 

0 

1

0 (-) 

0 (-) 

0 (-) 

0 (-) 

4 (1.00)

0.8 (1.00)

Minimum total annual takes within U.S. EEZ waters 0.8 (1.00)

STATUS OF STOCK

 The status of Blainville's beaked whales in Hawaiian waters relative to OSP is unknown, and there are 

insufficient data to evaluate trends in abundance. They are not listed as “threatened” or “endangered” under the 

Endangered Species Act (1973), nor as “depleted” under the MMPA. The Hawaiian stock of Blainville’s beaked 

whales is not considered strategic under the 1994 amendments to the MMPA because the estimated rate of fisheries 

related mortality or serious injury within the Hawaiian Islands EEZ (0.8 animals per year) is less than the PBR (9.6). 

However, the effect of potential interactions of unidentified beaked whales (which may have been Blainville’s 

beaked whales) with the Hawaii-based longline fishery in U.S. and international waters is not known. Insufficient 

information is available to determine whether the total fishery mortality and serious injury for Blainville’s beaked 

whales is insignificant and approaching zero mortality and serious injury rate. The increasing levels of 

anthropogenic noise in the world’s oceans has been suggested to be a habitat concern for whales (Richardson et al. 

1995), particularly for deep-diving whales like Blainville’s beaked whales that feed in the oceans’ “sound channel”. 

REFERENCES

Balcomb, K. C., III. 1987. The Whales of Hawaii. Marine Mammal Fund, 99 pp. 

Barlow, J. 2003. Cetacean abundance in Hawaiian waters during summer/fall 2002. Admin. Rep. LJ-03-13. 

Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La 

Jolla, CA 92037. 

Forney, K.A. 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994-2002. 

Admin. Rep. LJ-04-07. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92038. 17 pp. 

Frantzis, A. 1998. Does acoustic testing strand whales? Nature 392(5):29. 

Galbreath, E. C. 1963. Three beaked whales stranded on the Midway Islands, central Pacific Ocean. J. Mamm. 

44:422-423. 

Malakoff, D. 2002. Suit ties whale deaths to research cruise. Science 298:722-723. 

Martel, V. M. 2002. Summary of the report on the atypical mass stranding of beaked whales in the Canary Islands 

in September 2002 during naval exercises. Society for the Study of the Cetaceans in the Canary 

Archipelago (SECAC). Unpublished report. 11p. 

Mobley, J. R. , Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and 

abundance of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. 

Rep. LJ-00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 26 pp. 

Mead, J. G. 1989. Beaked whales of the genus Mesoplodon. In: S. H. Ridgway and R. Harrison (eds.), Handbook 

of Marine Mammals, Vol. 4: The River Dolphins and Larger Toothed Whales, pp. 349-430. Academic 

Press, 442 pp. 

NMFS 2001. Western Pacific Pelagic Fisheries Biological Opinion. Available from Pacific Islands Region, 1602 

Kapiolani Blvd, Suite 1110, Honolulu, HI 96814 (http://swr.nmfs.noaa.gov/pir). 

Nitta, E. 1991. The marine mammal stranding network for Hawaii: an overview. In: J.E. Reynolds III, D.K. Odell 

(eds.), Marine Mammal Strandings in the United States, pp.56-62. NOAA Tech. Rep. NMFS 98, 157 pp. 

249
Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

Perrin, W. F., G. P. Donovan and J. Barlow. 1994. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Special Issue 

15, 629 pp. 

Richardson, W. J., C. R. Greene, Jr., C. I. Malme, and D. H. Thompson. 1995. Marine Mammals and Noise. 

Academic Press, San Diego. 576 p. 

Shallenberger, E. W. 1981. The status of Hawaiian cetaceans. Final report to U.S. Marine Mammal Commission. 

MMC-77/23, 79pp. 

U.S. Department of Commerce and Secretary of the Navy. 2001. Joint Interim Report, Bahamas Marine Mammal 

Stranding Event of 15_16 March 2000. Available from NOAA, NMFS, Office of Protected Resources, 

Silver Spring, MD. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

250
Revised 03/15/2005 

CUVIER'S BEAKED WHALE (Ziphius cavirostris): Hawaiian Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

 Cuvier's beaked whales occur in 

all oceans and major seas (Heyning 

1989). In Hawaii, five strandings have 

been reported from Midway Islands, 

Pearl and Hermes Reef, Oahu, and 

Hawaii Islands (Shallenberger 1981; 

Galbreath 1963; Richards 1952; Nitta 

1991; Maldini 2005). Sightings have 

been reported off Lanai and Maui 

(Shallenberger 1981) and Hawaii, 

Ni’ihau, and Kauai (Mobley 2000, Baird 

et al. 2004). Four sightings were made 

during a 2002 shipboard survey of 

waters within the U.S. Exclusive 

Economic Zone (EEZ) of the Hawaiian 

islands (Figure 1; Barlow 2003). While 

nothing is known about stock structure, 

some genetic samples have been 

collected recently from around the island 

of Hawaii, and there have been resightings of individuals from the island 

of Hawaii (R.W. Baird, pers. comm.). 

For the Marine Mammal Protection Act 

(MMPA) stock assessment reports, 

Cuvier's beaked whales within the 

Pacific U.S. EEZ are divided into three discrete, non-contiguous areas: 1) Hawaiian waters (this report), 2) Alaskan 

waters, and 3) waters off California, Oregon and Washington. 

POPULATION SIZE

 Wade and Gerrodette (1993) made an estimate for Cuvier's beaked whales in the eastern tropical Pacific, 

but it is not known whether any of these animals are part of the same population that occurs around the Hawaiian 

Islands. As part of the Marine Mammal Research Program of the Acoustic Thermometry of Ocean Climate (ATOC) 

study, a total of twelve aerial surveys were conducted within about 25 nmi of the main Hawaiian Islands in 1993, 

1995 and 1998. Seven sightings of Cuvier’s beaked whales were made. An abundance estimate of 43 (CV=0.51) 

Cuvier’s beaked whales was calculated from the combined survey data (Mobley et al. 2000). This study 

underestimated the total number of Cuvier’s beaked whales within the U.S. EEZ off Hawaii, because areas around 

the Northwestern Hawaiian Islands (NWHI) and beyond 25 nautical miles from the main islands were not surveyed. 

Furthermore, this species is known to spend a large proportion of time diving, causing additional downward bias in 

the abundance estimate. The data on which this estimate was based are now over 5 years old. A 2002 shipboard 

line-transect survey of the entire Hawaiian Islands EEZ resulted in an abundance estimate of 12,728 (CV=0.83) 

Cuvier’s beaked whales (Barlow 2003), including a correction factor for missed diving animals. This is currently 

the best available abundance estimate for this stock. 

Minimum Population Estimate

 The log-normal 20th percentile of the 2002 abundance estimate is 6,919 Cuvier’s beaked whales. 

 

Current Population Trend

 No data are available on current population trend. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No data are available on current or maximum net productivity rate. 

W180 W175 W170 W165 W160 W155 W150

N10

N15

N20

N25

N30

N35

Figure 1. Cuvier’s beaked whale sighting locations during the 2002 

shipboard survey of U.S. EEZ waters surrounding the Hawaiian 

Islands (Barlow 2003; see Appendix 2 for details on timing and 

location of survey effort). Outer line represents approximate 

boundary of survey area and U.S. EEZ. 

251
POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size 

(6,919) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.50 

(for a species of unknown status with no known fishery mortality within the Hawaiian Islands EEZ; Wade and 

Angliss 1997), resulting in a PBR of 69 Cuvier’s beaked whales per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY 

Fishery Information 

 Information on fishery-related mortality of cetaceans in Hawaiian waters is limited, but the gear types used 

in Hawaiian fisheries are responsible for marine mammal mortality and serious injury in other fisheries throughout 

U.S. waters. Gillnets appear to capture marine mammals wherever they are used, and float lines from lobster traps 

and longlines can be expected to occasionally entangle whales (Perrin et al. 1994). 

 Interactions with cetaceans are reported for all pelagic fisheries (Nitta and Henderson 1993), but no takes of 

Cuvier's beaked whales have been documented. None were observed hooked or entangled in the Hawaii-based 

longline fishery between 1994 and 2002, with approximately 4-25% of all effort observed (Forney 2004). However, 

three unidentified cetaceans, which may have been Cuvier’s beaked whales, were taken in this fishery (Figure 2, 

Forney 2004). Since 2001, the Hawaii-based longline fishery has undergone a series of regulatory changes, 

primarily to protect sea turtles (NMFS 2001). Potential impacts of these regulatory changes on the rate of Cuvier’s 

beaked whale interactions are unknown. 

Other Mortality

 In recent years, there has been increasing concern that loud underwater sounds, such as active sonar and 

seismic operations, may be harmful to beaked whales (Malakoff 2002). The use of active sonar from military vessels 

has been implicated in mass strandings of beaked whales in the Mediterranean Sea during 1996 (Frantzis 1998), the 

Bahamas during 2000 (U.S. Dept. of Commerce and Secretary of the Navy 2001), and the Canary Islands 2002 

(Martel 2002). Similar military active sonar operations occur around the Hawaiian islands. No estimates of 

potential mortality or serious injury are available for U.S. waters. 

STATUS OF STOCK

 The status of Cuvier's beaked whales in Hawaiian waters relative to OSP is unknown, and there are 

insufficient data to evaluate trends in abundance. They are not listed as “threatened” or “endangered” under the 

Endangered Species Act (1973), nor as “depleted” under the MMPA. The Hawaiian stock of Cuvier’s beaked 

whales is not considered strategic under the 1994 amendments to the MMPA because there has been no reported 

fisheries related mortality within the Hawaiian Islands EEZ. However, the effect of potential interactions of 

unidentified beaked whales (which may have been Cuvier’s beaked whales) with the Hawaii-based longline fishery 

in U.S. and international waters is not known. Insufficient information is available to determine whether the total 

fishery mortality and serious injury for Cuvier’s beaked whales is insignificant and approaching zero mortality and 

serious injury rate. The increasing levels of anthropogenic noise in the world’s oceans has been suggested to be a 

habitat concern for whales (Richardson et al. 1995), particularly for deep-diving whales like Cuvier’s beaked whales 

that feed in the oceans’ “sound channel”. 

REFERENCES 

Baird, R.W., D.J. McSweeney, A.D. Ligon and D.L. Webster. 2004. Tagging feasibility and diving of Cuvier's 

beaked whales (Ziphius cavirostris) and Blainville's beaked whales (Mesoplodon densirostris) in Hawai'i.

Report prepared under Order No. AB133F-03-SE-0986 to the Hawai'i Wildlife Fund, Volcano, HI, from 

the Southwest Fisheries Science Center, National Marine Fisheries Service, La Jolla, CA, 92037 USA. 

Barlow, J. 2003. Cetacean abundance in Hawaiian waters during summer/fall 2002. Admin. Rep. LJ-03-13. 

Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La 

Jolla, CA 92037. 

Forney, K.A. 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994-2002. 

Admin. Rep. LJ-04-07. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92038. 17 pp. 

Frantzis, A. 1998. Does acoustic testing strand whales? Nature 392(5):29. 

Galbreath, E. C. 1963. Three beaked whales stranded on the Midway Islands, central Pacific Ocean. J. Mamm.

44:422-423. 

252
Heyning, J. E. 1989. Cuvier's beaked whale Ziphius cavirostris G. Cuvier, 1823. In: S. H. Ridgway and R. 

Harrison (eds.), Handbook of Marine Mammals, Vol. 4: The River Dolphins and Larger Toothed Whales, 

pp. 289-308. Academic Press, 442 pp. 

Malakoff, D. 2002. Suit ties whale deaths to research cruise. Science 298:722-723. 

Maldini, D., L. Mazzuca, and S. Atkinson. 2005. Odontocete stranding patterns in the Main Hawaiian Islands 

(1937-2002): How do they compare with live animal surveys? Pacific Science 59(1):55-67. 

Martel, V. M. 2002. Summary of the report on the atypical mass stranding of beaked whales in the Canary Islands 

in September 2002 during naval exercises. Society for the Study of the Cetaceans in the Canary 

Archipelago (SECAC). Unpublished report. 11p. 

Mobley, J. R. , Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and 

abundance of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. 

Rep. LJ-00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 26 pp. 

NMFS 2001. Western Pacific Pelagic Fisheries Biological Opinion. Available from Pacific Islands Region, 1602 

Kapiolani Blvd, Suite 1110, Honolulu, HI 96814 (http://swr.nmfs.noaa.gov/pir). 

Nitta, E. 1991. The marine mammal stranding network for Hawaii: an overview. In: J.E. Reynolds III, D.K. Odell 

(eds.), Marine Mammal Strandings in the United States, pp.56-62. NOAA Tech. Rep. NMFS 98, 157 pp. 

Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

Perrin, W.F., G. P. Donovan and J. Barlow. 1994. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Special Issue 

15, 629 pp. 

Richards, L. P. 1952. Cuvier's beaked whale from Hawaii. J. Mamm. 33:255. 

Richardson, W. J., C. R. Greene, Jr., C. I. Malme, and D. H. Thompson. 1995. Marine Mammals and Noise. 

Academic Press, San Diego. 576 p. 

Shallenberger, E. W. 1981. The status of Hawaiian cetaceans. Final report to U.S. Marine Mammal Commission. 

MMC-77/23, 79pp. 

U.S. Department of Commerce and Secretary of the Navy. 2001. Joint Interim Report, Bahamas Marine Mammal 

Stranding Event of 15_16 March 2000. Available from NOAA, NMFS, Office of Protected Resources, 

Silver Spring, MD. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

Wade, P. R. and T. Gerrodette. 1993. Estimates of cetacean abundance and distribution in the eastern tropical 

Pacific. Rep. Int. Whal. Commn. 43:477-493. 

253
Revised 03/15/2005 

LONGMAN’S BEAKED WHALE (Indopacetus pacificus): 

Hawaiian Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

 Longman’s beaked whale is 

considered one of the rarest and least 

known cetacean species (Jefferson et al. 

1993; Rice 1998; Dalebout et al 2003). 

Until recently, it was known only from 

two skulls found in Australia and 

Somalia (Longman 1926; Azzaroli 

1968). Recent genetic studies (Dalebout 

et al. 2003) have revealed that sightings 

of ‘tropical bottlenose whales’ 

(Hyperoodon sp.; Pitman et al. 1999) in 

the Indopacific region were in fact 

Longman’s beaked whales, providing 

the first description of the external 

appearance of this species. Although 

originally described as Mesoplodon 

pacificus (Longman 1926), it has been 

proposed that this species is sufficiently 

unique to be placed within its own 

genus, Indopacetus (Moore 1968; 

Dalebout et al. 2003). The distribution 

of Longman’s beaked whale, as 

determined from stranded specimens and 

sighting records of ‘tropical bottlenose 

whales’, includes tropical waters from 

the eastern Pacific westward through the 

Indian Ocean to the eastern coast of 

Africa. No strandings of Longman’s beaked whales have been documented in Hawaiian waters, although numerous 

strandings of unidentified beaked whales have been reported (Nitta 1991; Maldini 2005). One sighting of 

Longman’s beaked whale was made during a 2002 survey of waters within the U.S. Exclusive Economic Zone 

(EEZ) of the Hawaiian Islands (Figure 1; Barlow 2003). For the Marine Mammal Protection Act (MMPA) stock 

assessment reports, there is one Pacific stock of Longman’s beaked whales, found within waters of the Hawaiian 

Islands EEZ. 

POPULATION SIZE

 A 2002 shipboard line-transect survey of the entire Hawaiian Islands EEZ resulted in an abundance 

estimate of 766 (CV=1.05) Longman’s beaked whales (Barlow 2003). This is currently the best available 

abundance estimate for this stock. 

Minimum Population Estimate

 The log-normal 20th percentile of the 2002 abundance estimate is 371 Longman’s beaked whales. 

Current Population Trend

 No data are available on current population trend. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No data are available on current or maximum net productivity rate for Longman’s beaked whales. 

W180 W175 W170 W165 W160 W155 W150

N10

N15

N20

N25

N30

N35

Figure 1. Sighting locations of Indopacetus pacificus (triangle), 

Mesoplodon densirostris (circle) and unidentified Mesoplodon 

beaked whales (crosses) during the 2002 shipboard cetacean survey 

of U.S. waters surrounding the Hawaiian Islands (Barlow 2003; see 

Appendix 2 for details on timing and location of survey effort). 

Outer line indicates approximate boundary of survey area and U.S. 

EEZ.

254
POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size 

(371) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.50 

(for a stock of unknown status with no known fishery mortality or serious injury within the Hawaiian Islands EEZ; 

Wade and Angliss 1997), resulting in a PBR of 3.7 Longman’s beaked whales per year. 

HUMAN CAUSED MORTALITY AND SERIOUS INJURY 

Fishery Information

 Information on fishery-related 

mortality and serious injury of cetaceans 

in Hawaiian waters is limited, but the 

gear types used in Hawaiian fisheries are 

responsible for marine mammal mortality 

and serious injury in other fisheries 

throughout U.S. waters. Gillnets appear 

to capture marine mammals wherever 

they are used, and float lines from lobster 

traps and longlines can be expected to 

occasionally entangle whales (Perrin et 

al. 1994). 

 Interactions with cetaceans have 

been reported for all Hawaiian pelagic 

fisheries (Nitta and Henderson 1993), but 

none of these interactions are known to 

have involved Longman’s beaked 

whales. None were observed hooked or 

entangled in the Hawaii-based longline 

fishery between 1994 and 2002, with 

approximately 4-25% of all effort 

(measured as the number of sets made) 

observed by on-board observers (Forney 

2004). However, there were two 

interactions with unidentified whales that 

may have been Longman’s beaked 

whales (Figure 2). Since 2001, the 

Hawaii-based longline fishery has 

undergone a series of regulatory changes, 

primarily to protect sea turtles (NMFS 

2001). Potential impacts of these regulatory changes on the rate of Longman’s beaked whale interactions are 

unknown. 

Other Mortality

 In recent years, there has been increasing concern that loud underwater sounds, such as active sonar and 

seismic operations, may be harmful to beaked whales (Malakoff 2002). The use of active sonar from military vessels 

has been implicated in mass strandings of beaked whales in the Mediterranean Sea during 1996 (Frantzis 1998), the 

Bahamas during 2000 (U.S. Dept. of Commerce and Secretary of the Navy 2001), and the Canary Islands 2002 

(Martel, 2002). Similar military active sonar operations occur around the Hawaiian islands. No estimates of 

potential mortality or serious injury are available for U.S. waters.

STATUS OF STOCK

 The status of Longman's beaked whales in Hawaiian waters relative to OSP is unknown, and there are 

insufficient data to evaluate trends in abundance. They are not listed as “threatened” or “endangered” under the 

Endangered Species Act (1973), nor as “depleted” under the MMPA. The Hawaiian stock of Longman’s beaked 

whales is not considered strategic under the 1994 amendments to the MMPA, because there has been no reported 

fisheries related mortality or serious injury within the Hawaiian Islands EEZ. However, the effect of potential 

interactions of unidentified beaked whales (which may have been Longman’s beaked whales) with the Hawaii-based 

Figure 2. Locations of observed takes of possible Longman’s 

beaked whales (open diamonds) in the Hawaii-based longline fishery 

1994-2002. The solid lines represent the U.S. Exclusive Economic 

Zone (EEZ). 

255
longline fishery in U.S. and international waters is not known. Insufficient information is available to determine 

whether the total fishery mortality and serious injury for Longman’s beaked whales is insignificant and approaching 

zero mortality and serious injury rate. The increasing levels of anthropogenic noise in the world’s oceans has been 

suggested to be a habitat concern for whales (Richardson et al. 1995), particularly for deep-diving whales like 

Longman’s beaked whales that feed in the oceans’ “sound channel”. 

REFERENCES

Azzaroli, M. L. 1968. Second specimen of Mesoplodon pacificus, the rarest living beaked whale. Monitore 

Zoologico Italiano (N.S.) 2:67-79. 

Barlow, J. 2003. Cetacean abundance in Hawaiian waters during summer/fall 2002. Admin. Rep. LJ-03-13. 

Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La 

Jolla, CA 92038. 

Dalebout, M. L., G. J. B. Ross, C. S. Baker, R. C. Anderson, P. B. Best, V. G. Cockcroft, H. L. Hinsz, V. Peddemors 

and R. L. Pitman. 2003. Appearance, distribution and genetic distinctiveness of Longman’s beaked whale, 

Indopacetus pacificus. Marine Mammal Science 19:421-461. 

Forney, K.A. 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994-2002. 

Admin. Rep. LJ-04-07. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92037. 17 pp. 

Frantzis, A. 1998. Does acoustic testing strand whales? Nature 392(5):29. 

Jefferson, T. A., S. Leatherwood, and M. A. Webber. 1993. FAO species identification guide: marine mammals of 

the world. United States Environment Programme; Food and Agriculture Organization of the United 

Nations (FAO), Rome. 320p. 

Longman, H.A. 1926. New records of Cetacea, with a list of Queensland species. Memoirs of the Queensland 

Museum 8:266-278. 

Malakoff, D. 2002. Suit ties whale deaths to research cruise. Science 298:722-723 

Maldini, D., L. Mazzuca, and S. Atkinson. 2005. Odontocete stranding patterns in the Main Hawaiian Islands 

(1937-2002): How do they compare with live animal surveys? Pacific Science 59(1):55-67. 

Martel, V. M. 2002. Summary of the report on the atypical mass stranding of beaked whales in the Canary Islands 

in September 2002 during naval exercises. Society for the Study of the Cetaceans in the Canary 

Archipelago (SECAC). Unpublished report. 11p. 

Moore J. C. 1968. Relationships among the living genera of beaked whales. Fieldiana Zoology 53:209-298. 

NMFS 2001. Western Pacific Pelagic Fisheries Biological Opinion. Available from Pacific Islands Region, 1602 

Kapiolani Blvd, Suite 1110, Honolulu, HI 96814 (http://swr.nmfs.noaa.gov/pir). 

Nitta, E. 1991. The marine mammal stranding network for Hawaii: an overview. In: J.E. Reynolds III, D.K. Odell 

(eds.), Marine Mammal Strandings in the United States, pp.56-62. NOAA Tech. Rep. NMFS 98, 157 pp. 

Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

Perrin, W. F., G. P. Donovan and J. Barlow. 1994. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Special Issue 

15, 629 pp. 

Pitman, R. L., D. M. Palacios, P. L Brennan, K.C. III. Balcomb, and T. Miyashita. 1999. Sightings and possible 

identity of a bottlenose whale in the tropical Indo-Pacific: Indopacetus pacificus? Marine Mammal Science 

15:531-549. 

Rice, D. W. 1998. Marine Mammals of the world: systematics and distribution. Special Publication 4. The Society 

for Marine Mammalogy, Lawrence, KS, USA. 

Richardson, W. J., C. R. Greene, Jr., C. I. Malme, and D. H. Thompson. 1995. Marine Mammals and Noise. 

Academic Press, San Diego. 576 p. 

U.S. Department of Commerce and Secretary of the Navy. 2001. Joint Interim Report, Bahamas Marine Mammal 

Stranding Event of 15_16 March 2000. Available from NOAA, NMFS, Office of Protected Resources, 

Silver Spring, MD. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

256
Revised 03/15/2005 

PYGMY SPERM WHALE (Kogia breviceps): Hawaiian Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

 Pygmy sperm whales are found 

throughout the world in tropical and 

warm-temperate waters (Caldwell and 

Caldwell 1989). Between the years 

1949 and 2002, at least 22 strandings of 

this species were reported in the 

Hawaiian Islands (Tomich 1986; Nitta 

1991; Maldini 2005). A stranded calf 

was held for several days at Sea Life 

Park (Pryor 1975:94). Shallenberger 

(1981) reported three sightings off Oahu 

and Maui. Two sightings of pygmy or 

dwarf sperm whales were made between 

Hawaii and Maui during 1993-98 aerial 

surveys within about 25 nmi of the main 

Hawaiian Islands (Mobley et al. 2000). 

Two sightings were made during a 2002 

shipboard survey of waters within the 

U.S. Exclusive Economic Zone (EEZ) of 

the Hawaiian Islands (Figure 1; Barlow 

2003). Baird (2005) reported one 

sighting off Ni’ihau and another off the 

island off Hawaii (R.W. Baird, pers. 

comm.). Nothing is known about stock 

structure for this species. For the Marine 

Mammal Protection Act (MMPA) stock 

assessment reports, pygmy sperm whales 

within the Pacific U.S. EEZ are divided into two discrete, non-contiguous areas: 1) Hawaiian waters (this report), 

and 2) waters off California, Oregon and Washington. 

 

POPULATION SIZE

 As part of the Marine Mammal Research Program of the Acoustic Thermometry of Ocean Climate 

(ATOC) study, a total of twelve aerial surveys were conducted within about 25 nmi of the main Hawaiian Islands in 

1993, 1995 and 1998. Two sightings of five pygmy or dwarf sperm whales were made; however, these sightings 

were excluded during abundance analyses (Mobley et al. 2000), because they were made during poor observation 

conditions. A 2002 shipboard line-transect survey of the entire Hawaiian Islands EEZ resulted in an abundance 

estimate of 7,251 (CV=0.77) pygmy sperm whales (Barlow 2003), including a correction factor for missed diving 

animals. This is currently the best available abundance estimate for this stock. 

Minimum Population Estimate

 The log-normal 20th percentile of the 2002 abundance estimate is 4,082 pygmy sperm whales. 

 

Current Population Trend

 No data are available on current population trend. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No data are available on current or maximum net productivity rate. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size 

(4,082) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.50 

W180 W175 W170 W165 W160 W155 W150

N10

N15

N20

N25

N30

N35

Figure 1. Sighting locations of pygmy sperm whales (filled circle) 

and unidentified Kogia (cross) during the 2002 shipboard cetacean 

survey of U.S. EEZ waters surrounding the Hawaiian Islands 

(Barlow 2003; see Appendix 2 for details on timing and location of 

survey effort). Outer line indicates approximate boundary of survey 

area and U.S. EEZ.

257
(for a stock of unknown status with no known fishery mortality or serious injury within the Hawaiian Islands EEZ; 

Wade and Angliss 1997), resulting in a PBR of 41 pygmy sperm whales per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

 Information on fishery-related mortality of cetaceans in Hawaiian waters is limited, but the gear types used 

in Hawaiian fisheries are responsible for marine mammal mortality and serious injury in other fisheries throughout 

U.S. waters. Gillnets appear to capture marine mammals wherever they are used, and float lines from lobster traps 

and longlines can be expected to occasionally entangle whales (Perrin et al. 1994). Interactions with cetaceans have 

been reported for all Hawaiian pelagic fisheries (Nitta and Henderson 1993), but no interactions with pygmy sperm 

whales have been documented. None were observed hooked in the Hawaii-based longline fishery between 1994 and 

2002, with approximately 4-25% of all effort observed ( Forney 2004). 

STATUS OF STOCK 

The status of pygmy sperm whales in Hawaiian waters relative to OSP is unknown, and there are 

insufficient data to evaluate trends in abundance. They are not listed as “threatened” or “endangered” under the 

Endangered Species Act (1973), nor as “depleted” under the MMPA. The Hawaiian stock of pygmy sperm whales is 

not considered strategic under the 1994 amendments to the MMPA because there has been no reported fisheries 

related mortality or serious injury. Insufficient information is available to determine whether the total fishery 

mortality and serious injury for pygmy sperm whales is insignificant and approaching zero mortality and serious 

injury rate. The increasing levels of anthropogenic noise in the world’s oceans has been suggested to be a habitat 

concern for whales (Richardson et al. 1995), particularly for deep-diving whales like pygmy sperm whales that feed 

in the oceans’ “sound channel”. 

REFERENCES 

Baird, R.W. 2005. Sightings of dwarf (Kogia sima) and pygmy (K. breviceps) sperm whales from the main 

Hawaiian Islands. Pacific Science 59: in press.

Barlow, J. 2003. Cetacean abundance in Hawaiian waters during summer/fall 2002. Admin. Rep. LJ-03-13. 

Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La 

Jolla, CA 92037. 

Forney, K.A. 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994-2002. 

Admin. Rep. LJ-04-07. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92038. 17 pp. 

Caldwell, D. K. and M. C. Caldwell. 1989. Pygmy sperm whale Kogia breviceps (de Blainville, 1838): Dwarf 

sperm whale Kogia simus Owen, 1866. In: S. H. Ridgway and R. Harrison (eds.), Handbook of Marine 

Mammals, Vol. 4: The River Dolphins and Larger Toothed Whales, pp. 235-260. Academic Press, 442 pp. 

Maldini, D., L. Mazzuca, and S. Atkinson. 2005. Odontocete stranding patterns in the Main Hawaiian Islands 

(1937-2002): How do they compare with live animal surveys? Pacific Science 59(1):55-67. 

Mobley, J. R., Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and 

abundance of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. 

Rep. LJ-00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 26 pp. 

Nitta, E. 1991. The marine mammal stranding network for Hawaii: an overview. In: J.E. Reynolds III, D.K. Odell 

(eds.), Marine Mammal Strandings in the United States, pp.56-62. NOAA Tech. Rep. NMFS 98, 157 pp. 

Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

Perrin, W.F., G. P. Donovan and J. Barlow. 1994. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Special Issue 

15, 629 pp. 

Pryor, K. 1975. Lads Before the Wind: Adventures in Porpoise Training. Harper and Row, New York, 278 pp. 

Richardson, W. J., C. R. Greene, Jr., C. I. Malme, and D. H. Thompson. 1995. Marine Mammals and Noise. 

Academic Press, San Diego. 576 p. 

Shallenberger, E.W. 1981. The status of Hawaiian cetaceans. Final report to U.S. Marine Mammal Commission. 

MMC-77/23, 79pp. 

Tomich, P. Q. 1986. Mammals in Hawaii: A Synopsis and Notational Bibliography. Bishop Museum Press, Hawaii, 

375 pp. 

258
Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

259
Revised 03/15/2005

DWARF SPERM WHALE (Kogia sima): Hawaiian Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

 Dwarf sperm whales are found 

throughout the world in tropical to 

warm-temperate waters (Nagorsen 

1985). Rice (1998) recently argued that 

the species name simus, was incorrect 

and should be replaced by sima to reflect 

rules of Latin usage. At least four 

strandings of dwarf sperm whales have 

been documented in Hawaii (Tomich 

1986; Nitta 1991; Maldini 2005). Two 

sightings of pygmy or dwarf sperm 

whales were made between Hawaii and 

Maui during 1993-98 aerial surveys 

within about 25 nmi of the main 

Hawaiian Islands (Mobley et al. 2000). 

Five sightings of dwarf sperm whale 

were made during a 2002 shipboard 

survey of waters within the U.S. 

Exclusive Economic Zone (EEZ) of the 

Hawaiian Islands (Figure 1; Barlow 

2003). For the Marine Mammal 

Protection Act (MMPA) stock 

assessment reports, dwarf sperm whales 

within the Pacific U.S. EEZ are divided 

into two discrete, non-contiguous areas: 

1) Hawaiian waters (this report), and 2) 

waters off California, Oregon and 

Washington. 

 

POPULATION SIZE

 Wade and Gerrodette (1993) provided an estimate for the eastern tropical Pacific, but it is not known 

whether these animals are part of the same population that occurs in the central North Pacific. As part of the 

Marine Mammal Research Program of the Acoustic Thermometry of Ocean Climate (ATOC) study, a total of twelve 

aerial surveys were conducted within about 25 nmi of the main Hawaiian Islands in 1993, 1995 and 1998. Two 

sightings of five pygmy or dwarf sperm whales were made; however these sightings were excluded during 

abundance analyses (Mobley et al. 2000), because they were made during poor observation conditions. Therefore, 

no abundance was estimated from these surveys for dwarf sperm whales within Hawaiian waters. Baird (2005) 

reports that dwarf sperm whales are the sixth most commonly sighted odontocete around the Main Hawaiian Islands. 

This species’ small size, tendency to avoid vessels, deep-diving habits, combined with the high proportion of Kogia 

sightings that are not identified to species, may result in negatively biased relative abundances in this region (R.W. 

Baird, pers. comm.). A 2002 shipboard line-transect survey of the entire Hawaiian Islands EEZ resulted in an 

abundance estimate of 19,172 (CV=0.66) dwarf sperm whales (Barlow 2003), including a correction factor for 

missed diving animals. This is currently the best available abundance estimate for this stock. 

Minimum Population Estimate

 The log-normal 20th percentile of the 2002 abundance estimate is 11,555 dwarf sperm whales. 

 

Current Population Trend

 No data are available on current population trend. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No data are available on current or maximum net productivity rate. 

W180 W175 W170 W165 W160 W155 W150

N10

N15

N20

N25

N30

N35

Figure 1. Sighting locations of dwarf sperm whales (filled circle) 

and unidentified Kogia (cross) during the 2002 shipboard cetacean 

survey of U.S. waters surrounding the Hawaiian Islands (Barlow 

2003; see Appendix 2 for details on timing and location of survey 

effort). Outer line indicates approximate boundary of survey area 

and U.S. EEZ.

260
POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size 

(11,555) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.50 

(for a stock of unknown status with no known fishery mortality or serious injury within the Hawaiian Islands EEZ; 

Wade and Angliss 1997), resulting in a PBR of 116 dwarf sperm whales per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information

 Information on fishery-related mortality of cetaceans in Hawaiian waters is limited, but the gear types 

used in Hawaiian fisheries are responsible for marine mammal mortality and serious injury in other fisheries 

throughout U.S. waters. Gillnets appear to capture marine mammals wherever they are used, and float lines from 

lobster traps and longlines can be expected to occasionally entangle whales (Perrin et al. 1994). Interactions with 

cetaceans have been reported for all Hawaiian pelagic fisheries (Nitta and Henderson 1993), but no interactions with 

dwarf sperm whales have been documented. None were observed hooked in the Hawaii-based longline fishery 

between 1994 and 2002, with approximately 4-25% of all effort observed ( Forney 2004). 

STATUS OF STOCK

 The status of dwarf sperm whales in Hawaiian waters relative to OSP is unknown, and there are insufficient 

data to evaluate trends in abundance. They are not listed as “threatened” or “endangered” under the Endangered 

Species Act (1973), nor as “depleted” under the MMPA. The Hawaiian stock of dwarf sperm whales is not 

considered strategic under the 1994 amendments to the MMPA because there has been no reported fisheries related 

mortality or serious injury. Insufficient information is available to determine whether the total fishery mortality 

and serious injury for dwarf sperm whales is insignificant and approaching zero mortality and serious injury rate. 

The increasing levels of anthropogenic noise in the world’s oceans has been suggested to be a habitat concern for 

whales (Richardson et al. 1995), particularly for deep-diving whales like dwarf sperm whales that feed in the 

oceans’ “sound channel”. 

REFERENCES 

Baird, R.W. 2005. Sightings of dwarf (Kogia sima) and pygmy (K. breviceps) sperm whales from the main 

Hawaiian Islands. Pacific Science 59: in press.

Barlow, J. 2003. Cetacean abundance in Hawaiian waters during summer/fall 2002. Admin. Rep. LJ-03-13. 

Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La 

Jolla, CA 92037. 

Forney, K.A. 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994-2002. 

Admin. Rep. LJ-04-07. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92038. 17 pp. 

Maldini, D., L. Mazzuca, and S. Atkinson. 2005. Odontocete stranding patterns in the Main Hawaiian Islands 

(1937-2002): How do they compare with live animal surveys? Pacific Science 59(1):55-67. 

Mobley, J. R. , Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and 

abundance of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. 

Rep. LJ-00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 26 pp. 

Nagorsen, D. 1985. Kogia simus. Mamm. Spec. 239:1-6. 

Nitta, E. 1991. The marine mammal stranding network for Hawaii: an overview. In: J.E. Reynolds III, D.K. Odell 

(eds.), Marine Mammal Strandings in the United States, pp.56-62. NOAA Tech. Rep. NMFS 98, 157 pp. 

Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

Perrin, W.F., G. P. Donovan and J. Barlow. 1994. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Special Issue 

15, 629 pp. 

Rice, D.W. 1998. Marine Mammals of the World Systematics and Distribution. Special Publication Number 4 The 

Society of Marine Mammalogy. Douglas Wartzok (ed.). 231 pp. 

Richardson, W. J., C. R. Greene, Jr., C. I. Malme, and D. H. Thompson. 1995. Marine Mammals and Noise. 

Academic Press, San Diego. 576 p. 

Tomich, P. Q. 1986. Mammals in Hawaii: A Synopsis and Notational Bibliography. Bishop Museum Press, Hawaii, 

375 pp.

261
Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

Wade, P. R. and T. Gerrodette. 1993. Estimates of cetacean abundance and distribution in the eastern tropical 

Pacific. Rep. Int. Whal. Commn. 43:477-493. 

262
Revised 03/15/2005 

SPERM WHALE (Physeter macrocephalus): Hawaiian Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE 

 Sperm whales are widely 

distributed across the entire North 

Pacific and into the southern Bering Sea 

in summer but the majority are thought 

to be south of 40o

N in winter (Rice 

1974, 1989; Gosho et al. 1984; 

Miyashita et al. 1995). For 

management, the International Whaling 

Commission (IWC) had divided the 

North Pacific into two management 

regions (Donovan 1991) defined by a 

zig-zag line which starts at 150o

W at the 

equator, is 160o

W between 40-50oN, and 

ends up at 180o

W north of 50oN; 

however, the IWC has not reviewed this 

stock boundary in many years (Donovan 

1991). Summer/fall surveys in the 

eastern tropical Pacific (Wade and 

Gerrodette 1993) show that although 

sperm whales are widely distributed in 

the tropics, their relative abundance 

tapers off markedly westward towards 

the middle of the tropical Pacific (near 

the IWC stock boundary at 150o

W) and 

tapers off northward towards the tip of 

Baja California. The Hawaiian Islands 

marked the center of a major nineteenth century whaling ground for sperm whales (Gilmore 1959; Townsend 1935). 

Since 1936, at least 18 strandings have been reported from Oahu, Kauai and Kure Atoll (Woodward 1972; Nitta 

1991; Maldini 2005). Sperm whales have also been sighted around several of the Northwestern Hawaiian Islands 

(Rice 1960; Barlow 2003), off the main island of Hawaii (Lee 1993; Mobley et al. 2000) in the Kauai Channel and 

in the Alenuihaha Channel between Maui and the island of Hawaii (Shallenberger 1981). In addition, the sounds of 

sperm whales have been recorded throughout the year off Oahu (Thompson and Friedl 1982). A summer/fall 2002 

shipboard survey of waters within the U.S. Exclusive Economic Zone (EEZ) of the Hawaiian Islands resulted in 43 

sperm whale sightings throughout the study area (Figure 1; Barlow 2003). 

 The stock identity of sperm whales in the North Pacific has been inferred from historical catch records 

(Bannister and Mitchell 1980) and from trends in CPUE and tag-recapture data (Ohsumi and Masaki 1977), but 

much uncertainty remains. A 1997 survey designed specifically to investigate stock structure and abundance of 

sperm whales in the northeastern temperate Pacific revealed no apparent hiatus in distribution between the U.S. EEZ 

off California and areas farther west, out to Hawaii (Barlow and Taylor 1998). Very preliminary genetic analyses 

revealed significant differences between sperm whales off the coast of California, Oregon and Washington and those 

sampled offshore to Hawaii (Mesnick et al., unpubl. data); analyses of additional genetic samples are ongoing at the 

NMFS, Southwest Fisheries Science Center. For the Marine Mammal Protection Act (MMPA) stock assessment 

reports, sperm whales within the Pacific U.S. EEZ are divided into three discrete, non-contiguous areas: 1) waters 

around Hawaii (this report), 2) California, Oregon and Washington waters, and 3) Alaskan waters. 

POPULATION SIZE

 A large 1982 abundance estimate for the entire eastern North Pacific (Gosho et al. 1984) was based on a 

CPUE method which is no longer accepted as valid by the International Whaling Commission. A spring 1997 

combined visual and acoustic line-transect survey conducted in the eastern temperate North Pacific resulted in 

estimates of 24,000 (CV=0.46) sperm whales based on visual sightings, and 39,200 (CV=0.60) based on acoustic 

detections and visual group size estimates (Barlow and Taylor 1998). In the eastern tropical Pacific, the abundance 

of sperm whales has been estimated as 22,700 (95% C.I.=14,800-34,600; Wade and Gerrodette 1993). However, it 

W180 W175 W170 W165 W160 W155 W150

N10

N15

N20

N25

N30

N35

Figure 1. Sperm whale sighting locations during the 2002 shipboard 

survey of U.S. EEZ waters surrounding the Hawaiian Islands 

(Barlow 2003; see Appendix 2 for details on timing and location of 

survey effort). Outer line represents approximate boundary of survey 

area and U.S. EEZ. 

263
is not known whether any or all of these animals routinely enter the U.S. EEZ of the Hawaiian Islands. As part of 

the Marine Mammal Research Program of the Acoustic Thermometry of Ocean Climate (ATOC) study, a total of 

twelve aerial surveys were conducted within about 25 nmi of the main Hawaiian Islands in 1993, 1995 and 1998. 

An average abundance estimate of 66 (CV=0.56) sperm whales was calculated from the combined survey data 

(Mobley et al. 2000). This study underestimated the total number of sperm whales within the U.S. EEZ off Hawaii, 

because areas around the Northwestern Hawaiian Islands (NWHI) and beyond 25 nautical miles from the main 

islands were not surveyed. Furthermore, this species is known to spend a large proportion of time diving, causing 

additional downward bias in the abundance estimate. The data on which this estimate was based are now over 5 

years old. A 2002 shipboard line-transect survey of the entire Hawaiian Islands EEZ resulted in an abundance 

estimate of 7,082 (CV=0.30) sperm whales (Barlow 2003), including a correction factor for missed diving animals. 

This is currently the best available abundance estimate for this stock. 

Minimum Population Estimate

 The log-normal 20th percentile of the 2002 abundance estimate is 5,531 sperm whales. 

 

Current Population Trend

 No data on current population trend are available. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No data on current or maximum net productivity rate are available. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size 

(5,531 ) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.1 

(the default value for an endangered species; Wade and Angliss 1997), resulting in a PBR of 11 sperm whales per 

year. 

HUMAN-CAUSED MORTALITY AND 

SERIOUS INJURY

Fishery Information

 Information on fishery-related 

mortality of cetaceans in Hawaiian 

waters is limited, but the gear types used 

in Hawaiian fisheries are responsible for 

marine mammal mortality and serious 

injury in other fisheries throughout U.S. 

waters. Gillnets appear to capture marine 

mammals wherever they are used, and 

float lines from lobster traps and 

longlines can be expected to occasionally 

entangle whales (Perrin et al. 1994). 

 Interactions with cetaceans are 

reported for all pelagic fisheries, and 

large whales have been entangled in 

longlines off the Hawaiian Islands (Nitta 

and Henderson 1993; NMFS/PIR, 

unpublished data). Between 1994 and 

2002, one sperm whale was observed 

entangled within the Hawaiian Islands 

EEZ in the Hawaii-based longline 

fishery, with approximately 4-25% of all 

effort observed (Table 1; Forney 2004). 

During the 905 observed trips with 11,014 

sets, the average interaction rate of sperm 

whales was one animal per 905 fishing 

trips, or one animal per 11,014 sets. The 

Figure 2. Location of the observed sperm whale take in the Hawaiibased longline fishery, 1998-2002 (filled diamond), and the take 

observed during an experimental longline set in 2002 (open 

diamond). Solid lines represent the U.S. Exclusive Economic Zone 

(EEZ). 

264
caught animal was apparently able to free itself and was not considered seriously injured (Forney 2004), following 

established guidelines for assessing serious injury in marine mammals (Angliss and DeMaster 1998). The average 

5-yr estimate of annual mortality and serious injury within the Hawaiian Islands EEZ during 1998-2002 is zero 

sperm whales. One additional sperm whale was observed taken in an experimental set outside the U.S. EEZ, but the 

severity of its injuries could not be determined (Forney 2004). Since 2001, the Hawaii-based longline fishery has 

undergone a series of regulatory changes, primarily to protect sea turtles (NMFS 2001). Potential impacts of these 

regulatory changes on the rate of sperm whale interactions are unknown. 

 

Table 1. Summary of available information on incidental mortality and serious injury of sperm whales (Hawaiian 

stock) in commercial fisheries, within and outside of the Hawaiian Islands EEZ (Forney 2004). Mean annual takes 

are based on 1998-2002 data unless otherwise indicated; n/a = not available. 

Mortality and Serious Injury 

outside of U.S. EEZ

Mortality and Serious Injury 

within Hawaiian Islands EEZ

Fishery Name Year(s) Data Type

Percent 

Observer 

Coverage Observed

Estimated 

(CV in 

parentheses)

Mean Annual 

Takes 

(CV in 

parentheses)

Observed

Estimated 

(CV in 

parentheses)

Mean Annual 

Takes 

(CV in 

parentheses)

Hawaii-based 

longline fishery 

1998 

1999 

2000 

2001 

2002

1998-2002 

observer 

data

4.6% 

3.5% 

11.8% 

22.7% 

24.9%

0 

0 

0 

0 

0

0 (-) 

0 (-) 

0 (-) 

0 (-) 

0 (-)

0 (-)

0 

0 

0 

0 

0

0 (-) 

0 (-) 

0 (-) 

0 (-) 

0 (-)

0 (-)

Experimental 

longline fishery 2002 observed 1 n/a 0.2 (n/a) 

Minimum total annual takes within U.S. EEZ waters 0 (-)

 

Historical Mortality

 Between 1800 and 1909, about 60,842 sperm whales were estimated taken in the North Pacific (Best 1976). 

The reported take of North Pacific sperm whales by commercial whalers between 1947 and 1987 totaled 258,000 (C. 

Allison, pers. comm.). Factory ships operated as far south as 20o

N (Ohsumi 1980). Ohsumi (1980) lists an additional 

28,198 sperm whales taken mainly in coastal whaling operations from 1910 to 1946. Based on the massive underreporting of Soviet catches, Brownell et al. (1998) estimate that about 89,000 whales were additionally taken by the 

Soviet pelagic whaling fleet between 1949 and 1979. The Japanese coastal operations apparently also underreported catches by an unknown amount (Kasuya 1998). Thus a total of at least 436,000 sperm whales were taken 

between 1800 and the end of commercial whaling for this species in 1987. Of this grand total, an estimated 33,842 

were taken by Soviet and Japanese pelagic whaling operations in the eastern North Pacific from the longitude of 

Hawaii to the U.S. West coast, between 1961 and 1976 (Allen 1980, IWC statistical Areas II and III), and 965 were 

reported taken in land-based U.S. West coast whaling operations between 1947 and 1971 (Ohsumi 1980). In 

addition, 13 sperm whales were taken by shore whaling stations in California between 1919 and 1926 (Clapham et 

al. 1997). There has been a prohibition on taking sperm whales in the North Pacific since 1988, but large-scale 

pelagic whaling stopped earlier, in 1980. Some of the whales taken during the whaling era were certainly from a 

population or populations that occur within Hawaiian waters. 

STATUS OF STOCK

 The only estimate of the status of North Pacific sperm whales in relation to carrying capacity (Gosho et al. 

1984) is based on a CPUE method which is no longer accepted as valid. The status of sperm whales in Hawaiian 

waters relative to OSP is unknown, and there are insufficient data to evaluate trends in abundance. Sperm whales are 

formally listed as "endangered" under the Endangered Species Act (ESA), and consequently the Hawaiian stock is 

automatically considered as a "depleted" and "strategic" stock under the MMPA. Insufficient information is 

available to determine whether the total fishery mortality and serious injury for sperm whales is insignificant and 

approaching zero mortality and serious injury rate. Furthermore, the effect of interactions with the Hawaii-based 

longline fishery in U.S. and international waters is not known. The increasing levels of anthropogenic noise in the 

world’s oceans has been suggested to be a habitat concern for whales (Richardson et al. 1995), particularly for deepdiving whales like sperm whales that feed in the oceans’ “sound channel”. 

265
REFERENCES

Angliss, R. P. and D. P. DeMaster. 1998. Differentiating Serious and Non_Serious Injury of Marine Mammals 

Taken Incidental to Commercial Fishing Operations: Report of the Serious Injury Workshop 1_2 April 

1997, Silver Spring, Maryland. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR-13. 48 pp. 

Allen, K. R. 1980. Size distribution of male sperm whales in the pelagic catches. Rep. Int. Whal. Commn. Special 

Issue 2:51-56. 

Allison, C. International Whaling Commission. The Red House, 135 Station Road, Impington, Cambridge, UK CB4 

9NP. 

Barlow, J. 2003. Cetacean abundance in Hawaiian waters during summer/fall 2002. Admin. Rep. LJ-03-13. 

Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La 

Jolla, CA 92037. 

Barlow, J. and B. L. Taylor. 1998. Preliminary abundance of sperm whales in the northeastern temperate Pacific 

estimated from a combined visual and acoustic survey. Paper SC/50/CAWS20 presented to the 

International Whaling Commission, June 1998 (unpublished). xx pp. 

Bannister, J. and E. Mitchell. 1980. North Pacific sperm whale stock identity: distributional evidence from Maury 

and Townsend charts. Rep. Int. Whal. Commn. (Spec. Iss. 2):219-230. 

Best, P. B. 1976. A review of world sperm whale stocks. Paper ACMRR/MM/SC/8 Rev. 1, FAO Scientific 

Consultation of Marine Mammals, Bergen, Norway. 

Brownell, R. L., Jr., A. V. Yablokov and V. A. Zemmsky. 1998. USSR pelagic catches of North Pacific sperm 

whales, 1949-1979: Conservation implications. Paper SC/50/CAWS27 presented to the International 

Whaling Commission, June 1998 (unpublished). 

Clapham, P. J., S. Leatherwood, I. Szczepaniak, and R. L. Brownell, Jr. 1997. Catches of humpback and other 

whales from shore stations at Moss Landing and Trinidad, California, 1919-1926. Marine Mammal 

Science 13(3):368-394. 

Donovan, G. P. 1991. A review of IWC stock boundaries. Rept. Int. Whal. Commn., Special Issue 13:39-68. 

Forney, K.A. 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994-2002. 

Admin. Rep. LJ-04-07. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92037. 17 pp. 

Gilmore, R. M. 1959. On the mass strandings of sperm whales. Pac. Nat. 1(9-10):3-15. 

Gosho, M. E., D. W. Rice, and J. M. Breiwick. 1984. The sperm whale Physeter macrocephalus. Mar. Fish. Rev. 

46(4):54-64. 

Kasuya, T. 1998. Evidence of statistical manipulations in Japanese coastal sperm whale fishery. Paper 

SC/50/CAWS10 presented to the International Whaling Commission, June 1998 (unpublished). 

Lee, T. 1993. Summary of cetacean survey data collected between the years of 1974 and 1985. NOAA Tech.Mem. 

NMFS 181, 184pp. 

Maldini, D., L. Mazzuca, and S. Atkinson. 2005. Odontocete stranding patterns in the Main Hawaiian Islands 

(1937-2002): How do they compare with live animal surveys? Pacific Science 59(1):55-67. 

Mesnick, S. Southwest Fisheries Science Center, NMFS, 8604 La Jolla Shores Drive, La Jolla, California, 92037. 

Miyashita, T., H. Kato, and T. Kasuya (Eds.). 1995. Worldwide map of cetacean distribution based on Japanese 

sighting data. Volume 1. National Research Institute of Far Seas Fisheries, Shizuoka, Japan. 140pp. 

Mobley, J. R. , Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and 

abundance of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. 

Rep. LJ-00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 26 pp. 

NMFS, Pacific Islands Region, 1602 Kapiolani Blvd, Suite 1110, Honolulu, HI 96814. 

NMFS 2001. Western Pacific Pelagic Fisheries Biological Opinion. Available from Pacific Islands Region, 1602 

Kapiolani Blvd, Suite 1110, Honolulu, HI 96814 (http://swr.nmfs.noaa.gov/pir). 

Nitta, E. 1991. The marine mammal stranding network for Hawaii: an overview. In: J.E. Reynolds III, D.K. Odell 

(eds.), Marine Mammal Strandings in the United States, pp.56-62. NOAA Tech. Rep. NMFS 98, 157 pp. 

Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

Ohsumi, S. 1980. Catches of sperm whales by modern whaling in the North Pacific. Rep. Int. Whal. Commn. 

(Spec. Iss. 2):11-18. 

Ohsumi, S. and Y. Masaki. 1977. Stocks and trends of abundance of the sperm whale in the North Pacific. Rep. 

Int. Whal. Commn. 27:167-175. 

266
Perrin, W.F., G. P. Donovan and J. Barlow. 1994. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Special Issue 

15, 629 pp. 

Rice, D. W. 1960. Distribution of the bottle-nosed dolphin in the leeward Hawaiian Islands. J. Mamm. 41:407-

408. 

Rice, D. W. 1974. Whales and whale research in the eastern North Pacific. pp. 170-195 In: W. E. Schevill (ed.). 

The Whale Problem: A Status Report. Harvard Press, Cambridge, MA. 

Rice, D. W. 1989. Sperm whale Physeter macrocephalus Linneaus, 1758. In: S. H. Ridgway and R. Harrison 

(eds.), Handbook of Marine Mammals, Vol. 4: The River Dolphins and Larger Toothed Whales, pp. 177-

233. Academic Press, 442 pp. 

Richardson, W. J., C. R. Greene, Jr., C. I. Malme, and D. H. Thompson. 1995. Marine Mammals and Noise. 

Academic Press, San Diego. 576 p. 

Shallenberger, E.W. 1981. The status of Hawaiian cetaceans. Final report to U.S. Marine Mammal Commission. 

MMC-77/23, 79pp. 

Thompson, P. O. and W. A. Friedl. 1982. A long term study of low frequency sound from several species of whales 

off Oahu, Hawaii. Cetology 45:1-19. 

Townsend, C. H. 1935. The distribution of certain whales as shown by logbook records of American whaleships. 

Zoologica 19:1-50. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

Wade, P. R. and T. Gerrodette. 1993. Estimates of cetacean abundance and distribution in the eastern tropical 

Pacific. Rep. Int. Whal. Commn. 43:477-493. 

Woodward, P. W. 1972. The natural history of Kure Atoll, northwestern Hawaiian Islands. Atoll Res. Bull. 

164:302. 

267
Revised 03/15/2005 

BLUE WHALE (Balaenoptera musculus): Western North Pacific Stock 

 

STOCK DEFINITION AND GEOGRAPHIC RANGE

 

 The International Whaling 

Commission (IWC) has formally 

considered only one management stock

for blue whales in the North Pacific

(Donovan 1991), but up to five

populations have been proposed (Reeves

et al. 1998). Rice (1974) hypothesized 

that blue whales from Baja California

migrated far offshore to fed in the eastern

Aleutians or Gulf of Alaska and returned

to feed in California waters; however, he 

has more recently concluded that the

California population is separate from the 

Gulf of Alaska population (Rice 1992).

Length frequency analyses (Gilpatrick et

al. 1996) and photo-identification studies 

(Calambokidis et al. 1995) support

separate population status for blue

whales feeding off California and those

feeding in Alaskan waters. Whaling

catch data indicate that whales feeding

along the Aleutian Islands are probably 

part of a central Pacific stock (Reeves et

al. 1998), which may migrate to offshore

waters north of Hawaii in winter (Berzin

and Rovnin 1966). Blue whale feeding 

aggregations have not been found in

Alaska despite several surveys

(Leatherwood et al. 1982; Stewart et al. 

1987; Forney and Brownell 1996);

however, blue whale calls have been recorded there between 1995 and 2001 (Stafford et al. 2001, Stafford 2003).

Recent analyses of acoustic

Figure 1. Locations of two blue whale sightings made by observers

aboard Hawaii-based longline fishing vessels in July 1994 and 

February 1997 (NMFS/PIR unpublished data). Solid lines represent 

the U.S. Exclusive Economic Zone (EEZ). 

 data obtained throughout the North Pacific Ocean (Stafford et al. 2001; 

Stafford 2003) has revealed two distinct blue whale call types, suggesting two North Pacific stocks: eastern and 

western. The regional occurrence patterns indicate that blue whales from the eastern North Pacific stock winter off 

Mexico, central America, and as far south as 8°S (Stafford et al. 1999), and feed during summer off the U. S. West

Coast and to a lesser extent in the Gulf of Alaska, and in central North Pacific waters. This stock has previously

been documented to feed in waters off California (and occasionally as far north as British Columbia; Calambokidis 

et al. 1998) in summer/fall (from June to November) migrating south to productive areas off Mexico (Calambokidis 

et al. 1990) and as far south as the Costa Rica Dome (10° N) in winter/spring (Mate et al. 1999, Stafford et al. 1999).

Blue whales belonging to the western Pacific stock appear to feed in summer southwest of Kamchatka, south of the

Aleutians, and in the Gulf of Alaska (Stafford 2003; Watkins et al. 2000), and in winter they migrate to lower 

latitudes in the western Pacific and less frequently in the central Pacific, including Hawaii (Stafford et al. 2001). The 

only published sighting record of blue whales near Hawaii is that of Berzin and Rovnin (1966). Two sightings have

been made by observers on Hawaii-based longline vessels (Figure 1; NMFS/PIR, unpublished data). Additional 

evidence that blue whales occur in this area comes from acoustic recordings made off Oahu and Midway Islands 

(Northrop et al. 1971; Thompson and Friedl 1982), which included at least some within the U.S. Exclusive 

Economic Zone (EEZ). The recordings made off Hawaii showed bimodal peaks throughout the year (Stafford et al. 

2001), with western Pacific call types heard during winter and eastern Pacific calls heard during summer. For the

Marine Mammal Protection Act (MMPA) stock assessment reports, there are two blue whale stocks within the 

268
Pacific U.S. EEZ: 1) the western North Pacific stock (this report), which includes whales found around the Hawaiian 

Islands during winter, 2) the eastern North Pacific stock, which feeds primarily off California.

POPULATION SIZE

 From ship line-transect surveys, Wade and Gerrodette (1993) estimated 1,400 blue whales for the eastern 

tropical Pacific. A weighted average estimate of 1,744 blue whales is available for California, Oregon and 

Washington, based on shipboard line-transect surveys in 1996 and 2002(Barlow 2003a) and photographic markrecapture estimates (Calambokidis et al. 2003 ). No data are available to estimate population size for any other 

North Pacific blue whale population, including the putative central stock that apparently summered along the 

Aleutians and wintered north of Hawaii. No blue whale sightings were made during a summer 1994 shipboard 

survey south of the Aleutian Islands (Forney and Brownell 1996), during twelve aerial surveys conducted in 1993-

98 within about 25 nmi of the main Hawaiian Islands (Mobley et al. 2000), or during a summer/fall 2002 shipboard 

surveys of the entire Hawaiian Islands EEZ (Barlow 2003b). Therefore, no estimate of abundance is available for 

the western Pacific blue whale stock. 

Minimum Population Estimate

 No data are available to provide a minimum population estimate. 

Current Population Trend 

 No data are available on current population trend. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES 

No data are available on current or maximum net productivity rate.

POTENTIAL BIOLOGICAL REMOVAL

 No PBR can be calculated for this stock at this time. 

 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information 

 Information on fishery-related mortality of cetaceans in Hawaiian waters is limited, but the gear types used 

in Hawaiian fisheries are responsible for marine mammal mortality and serious injury in other fisheries throughout 

U.S. waters. Gillnets appear to capture marine mammals wherever they are used, and float lines from lobster traps 

and longlines can be expected to occasionally entangle whales (Perrin et al. 1994). Large whales have been 

entangled in longline gear off the Hawaiian Islands (Nitta and Henderson 1993, Forney 2004), but no interactions 

with blue whales were observed in the Hawaii-based longline fishery between 1994 and 2002, with approximately 4-

25% of all effort observed (Forney 2004).

 

Historical Mortality

 At least 9,500 blue whales were taken by commercial whalers throughout the North Pacific between 1910 

and 1965 (Ohsumi and Wada 1972). Some proportion of this total may have been from a population or populations 

that migrate seasonally into the Hawaiian EEZ. The species has been protected in the North Pacific by the IWC 

since 1966.

STATUS OF STOCK 

The status of blue whales in Hawaiian waters relative to OSP is unknown, and there are insufficient data to 

evaluate trends in abundance. Blue whales are formally listed as "endangered" under the Endangered Species Act 

(ESA), and consequently the Hawaiian stock is automatically considered as a "depleted" and "strategic" stock under 

the MMPA. Insufficient information is available to determine whether the total fishery mortality and serious injury 

for blue whales is insignificant and approaching zero mortality and serious injury rate. Increasing levels of 

anthropogenic noise in the world’s oceans has been suggested to be a habitat concern for blue whales (Reeves et al. 

1998). 

REFERENCES 

Barlow, J. 2003a. Preliminary estimates of cetacean abundance off the U.S. West Coast: 1991-2001. Admin. Rept. 

LJ-03-03. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores 

Drive, La Jolla, CA, 92037. 26 pp. 

269
Barlow, J. 2003b. Cetacean abundance in Hawaiian waters during summer/fall 2002. Admin. Rep. LJ-03-13. 

Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La 

Jolla, CA 92037. 

Berzin, A. A. and A. A. Rovnin. 1966. Distribution and migration of whales in the northeastern part of the Pacific 

Ocean, Bering and Chukchi Seas. Izv. Tikhookean. Nauchno-issled, Inst. Rybn. Khoz. Okeanogr. 

(TINRO) 58:179-207. {In Russian}. (Translated by U.S. Dep. Inter., Bur. Commer. Fish., Seattle, 

Washington, 1966, pp. 103-106 In: Panin, K. I. (ed) Soviet Research on marine mammals of the Far East). 

Calambokidis, J, T. Chandler, K. Rasmussen, G.H. Steiger, and L. Schlender. 1998. Humpback and blue whale 

photographic identification: Report of research in 1997. Final report to Southwest Fisheries Science 

Center, Olympic Coast National Marine Sanctuary, University of California at Santa Cruz, and Cornell 

University. Cascadia Research, 2181⁄2 W. Fourth Ave., Olympia, WA 98501. 41pp. 

Calambokidis, J, T. Chandler, L. Schlender, G.H. Steiger, and A Douglas. 2003. Research on humpback and blue 

whale off California, Oregon and Washington in 2002. Final contract report to Southwest Fisheries Science 

Center, National Marine Fisheries Service. 8604 La Jolla Shores Drive, La Jolla, CA 92037. 49pp. 

Calambokidis, J., R. Sears, G. H. Steiger, and J. Evenson. 1995. Movement and stock structure of blue whales in the 

eastern North Pacific. P.19 In: Proceedings of the Eleventh Biennial Conference on the Biology of Marine 

Mammals, Orlando, FL, 14-18 December 1995 (Abstract). Society for Marine Mammalogy, Lawrence, KS. 

Calambokidis, J., G. H. Steiger, J.C. Cubbage, K.C. Balcomb, C. Ewald, S. Kruse, R. Wells, and R. Sears. 1990. 

Sightings and movement of blue whales off central California 1986-88 from photo-identification of 

individuals. Rep. Int. Whaling. Commn., Special Issue 12:343-348. 

Donovan, G. P. 1991. A review of IWC stock boundaries. Rept. Int. Whal. Commn., Special Issue 13:39-68. 

Forney, K.A. 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994-2002. 

Admin. Rep. LJ-04-07. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92037. 17 pp. 

Forney, K. A. and Brownell, R. L., Jr. 1996. Preliminary report of the 1994 Aleutian Island Marine Mammal 

Survey. Paper SC/48/O11 presented to the International Whaling Commission, June 1996 (unpublished). 

Gilpatrick, J., W. Perryman, M. Lynn, and M. A. DeAngelis. 1996. Geographic populations of blue whales 

(Balaenoptera musculus) in the North Pacific Ocean investigated from whaling records and aerial 

photogrammetry. Paper SC/47/NP4 presented to the International Whaling Commission, May 1995 

(unpublished). 

Leatherwood, S., R. R. Reeves, W. F. Perrin, and W. E. Evans. 1982. Whales, dolphins, and porpoises of the 

eastern North Pacific and adjacent Arctic waters: A guide to their identification. NOAA Technical Rept. 

NMFS Circular 444. 245 pp. 

Mate, B.R., B.A. Lagerquist, and J. Calambokidis. Movements of North Pacific blue whales during the feeding 

season off southern California and their southern fall migration. Mar. Mamm. Sci. 15(4):1246-1257. 

Mobley, J. R. , Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and 

abundance of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. 

Rep. LJ-00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 26 pp. 

Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

NMFS, Pacific Islands Region, Observer Pogram, 1602 Kapiolani Blvd, Suite 1110, Honolulu, HI 96814. 

Northrop, J., W. C. Cummings, and M. F. Morrison. 1971. Underwater 20-Hz signals recorded near Midway 

Island. J. Acoust. Soc. Am. 49:1909-1910. 

Ohsumi, S. and S. Wada. 1972. Stock assessment of blue whales in the North Pacific. Int. Whal. Commn. Sci. 

Comm. Rep., 20 pp. 

Perrin, W.F., G.P. Donovan and J. Barlow. 1994. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Spec. Iss. 15, 

629pp. 

Reeves, R. R., P. J. Clapham, R. L. Brownell, Jr., and G. K. Silber. 1998. Recovery plan for the blue whale 

(Balaenoptera musculus). Office of Protected Resources, NMFS, NOAA, Silver Spring, Maryland. 30 pp. 

Rice, D. W. 1974. Whales and whale research in the eastern North Pacific. pp. 170-195 In: W. E. Schevill (ed.). 

The Whale Problem: A Status Report. Harvard Press, Cambridge, MA. 

Rice, D. W. 1992. The blue whales of the southeastern North Pacific Ocean. pp. 1-3 In. Alaska Fisheries Science 

Center, Quart. Rept. Oct.-Dec. 

270
Stafford, K.M., S.L. Nieukirk, and C.G. Fox. 1999. An acoustic link between blue whales in the eastern tropical 

Pacific and the northeast Pacific. Mar. Mamm. Sci. 15(4):1258-1268. 

Stafford, K.M., S. L. Nieukirk, and G.G. Fox. 2001. Geographic and seasonal variation of blue whale calls in the 

North Pacific. J. Cetacean Res. Manage. 3(1):65-76. 

Stafford. K.M. 2003. Two types of blue whale calls recorded in the Gulf of Alaska. Mar. Mamm. Sci. 19:682-693 

Stewart, B. S., S. A. Karl, P. K. Yochem, S. Leatherwood, and J. L. Laake. 1987. Aerial surveys for cetaceans in 

the former Akutan, Alaska, whaling grounds. Arctic 40(1):33-42. 

Thompson, P. O. and W. A. Friedl. 1982. A long term study of low frequency sound from several species of whales 

off Oahu, Hawaii. Cetology 45:1-19. 

Wade, P. R. and T. Gerrodette. 1993. Estimates of cetacean abundance and distribution in the eastern tropical 

Pacific. Rep. Int. Whal. Commn. 43:477-493. 

Watkins, W. A., J. E. George, M. A. Daher, K. Mullin, D. L. Martin, S. H. Haga, and N. A. DiMarzio. 2000. Whale 

call data for the North Pacific November 1995 through July 1999: Occurrence of calling whales and source 

locations from SOSUS and other acoustic systems. Technical Report WHOI_00_02 available from Woods 

Hole Oceanographic Institution. 160pp. 

271
Revised 03/15/2005 

FIN WHALE (Balaenoptera physalus): Hawaiian Stock

STOCK DEFINITION AND GEOGRAPHIC RANGE

Fin whales are found 

throughout all oceans and seas of the 

world from tropical to polar latitudes. 

They have been considered rare in 

Hawaiian waters. Balcomb (1987) 

observed 8-12 fin whales in a 

multispecies feeding assemblage on 20 

May 1966 approx. 250 mi. south of 

Honolulu. Additional sightings were 

reported north of Oahu in May 1976 and 

in the Kauai Channel in February 1979 

(Shallenberger 1981). More recently, a 

single fin whale was observed north of 

Kauai in February 1994 (Mobley et al. 

1996), and five sightings were made 

during a 2002 survey of waters within 

the U.S. Exclusive Economic Zone 

(EEZ) of the Hawaiian Islands (Barlow 

2003; Figure 1). A single stranding has 

been reported on Maui (Shallenberger 

1981). Thompson and Friedl (1982; and 

see Northrop et al. 1968) suggested that 

fin whales migrate into Hawaiian waters 

mainly in fall and winter, based on 

acoustic recordings off Oahu and 

Midway Islands. Although the exact positions of the whales producing the sounds could not be determined, at least 

some of them were almost certainly within the U.S. EEZ. More recently, McDonald and Fox (1999) reported an 

average of 0.027 calling fin whales per 10002

 km (grouped by 8-hr periods) based on passive acoustic recordings 

within about 16 km of the north shore of Oahu. 

 The International Whaling Commission (IWC) recognized two stocks of fin whales in the North Pacific: 

the East China Sea and the rest of the North Pacific (Donovan 1991). Mizroch et al. (1984) cites evidence for 

additional fin whale subpopulations in the North Pacific. There is still insufficient information to accurately 

determine population structure, but from a conservation perspective it may be risky to assume panmixia in the entire 

North Pacific. In the North Atlantic, fin whales were locally depleted in some feeding areas by commercial whaling 

(Mizroch et al. 1984), in part because subpopulations were not recognized. The Marine Mammal Protection Act 

(MMPA) stock assessment reports recognize three stocks of fin whales in the North Pacific: 1) the Hawaii stock 

(this report), 2) the California/Oregon/Washington stock, and 3) the Alaska stock. 

POPULATION SIZE

 As part of the Marine Mammal Research Program of the Acoustic Thermometry of Ocean Climate 

(ATOC) study, a total of twelve aerial surveys were conducted within about 25 nmi of the main Hawaiian Islands in 

1993-98 (Mobley et al. 2000). Only one sighting of a single fin whale was made (Mobley et al. 1996), and no 

abundance estimate was calculated. Using passive acoustic detections from a hydrophone north of Oahu, 

MacDonald and Fox (1999) estimate an average density of 0.027 calling fin whales per 1000 km2

 within about 16 

km from shore. However, the relationship between the number of whales present and the number of calls detected is 

not known, and therefore this acoustic method does not provide an estimate of absolute abundance for fin whales. A 

2002 shipboard line-transect survey of the entire Hawaiian Islands EEZ resulted in an abundance estimate of 174 

(CV=0.72) fin whales (Barlow 2003). This is currently the best available abundance estimate for this stock. 

Minimum Population Estimate

 The log-normal 20th percentile of the 2002 abundance estimate is 101 fin whales. 

W180 W175 W170 W165 W160 W155 W150

N10

N15

N20

N25

N30

N35

Figure 1. Fin whale sighting locations during the 2002 shipboard 

survey of U.S. EEZ waters surrounding the Hawaiian Islands 

(Barlow 2003; see Appendix 2 for details on timing and location of 

survey effort). Outer line represents approximate boundary of survey 

area and U.S. EEZ. 

272
 

Current Population Trend 

 No data are available on current population trend. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES 

No data are available on current or maximum net productivity rate.

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size 

(101) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.1 

(the default value for an endangered species; Wade and Angliss 1997), resulting in a PBR of 0.2 fin whales per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information 

 Information on fishery-related mortality of cetaceans in Hawaiian waters is limited, but the gear types used 

in Hawaiian fisheries are responsible for marine mammal mortality and serious injury in other fisheries throughout 

U.S. waters. Gillnets appear to capture marine mammals wherever they are used, and float lines from lobster traps 

and longlines can be expected to occasionally entangle whales (Perrin et al. 1994). Interactions with cetaceans are 

reported for all pelagic fisheries, and large whales have been entangled in longline gear off the Hawaiian Islands 

(Nitta and Henderson 1993, Forney 2004). Between 1994 and 2002, no interactions with fin whales were observed 

in the Hawaii-based longline fishery, with approximately 4-25% of all effort observed (Forney 2004). 

Historical Mortality

 Large numbers of fin whales were taken by commercial whalers throughout the North Pacific from the 

early 20th century until the 1970s (Tønnessen and Johnsen 1982). Approximately 46,000 fin whales were taken 

from the North Pacific by commercial whalers between 1947 and 1987 (C. Allison, IWC, pers. comm.). Some of 

the whales taken may have been from a population or populations that migrate seasonally into the Hawaiian EEZ. 

The species has been protected in the North Pacific by the IWC since 1976.

STATUS OF STOCK 

The status of fin whales in Hawaiian waters relative to OSP is unknown, and there are insufficient data to 

evaluate trends in abundance. Fin whales are formally listed as "endangered" under the Endangered Species Act 

(ESA), and consequently the Hawaiian stock is automatically considered as a "depleted" and "strategic" stock under 

the MMPA. Insufficient information is available to determine whether the total fishery mortality and serious injury 

for fin whales is insignificant and approaching zero mortality and serious injury rate. The increasing levels of 

anthropogenic noise in the world’s oceans has been suggested to be a habitat concern for whales (Richardson et al. 

1995). 

REFERENCES

Allison, C. International Whaling Commission. The Red House, 135 Station Road, Impington, Cambridge, UK CB4 

9NP. 

Balcomb, K. C., III. 1987. The Whales of Hawaii. Marine Mammal Fund, 99 pp. 

Barlow, J. 2003. Cetacean abundance in Hawaiian waters during summer/fall 2002. Admin. Rep. LJ-03-13. 

Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La 

Jolla, CA 92037. 

Donovan, G. P. 1991. A review of IWC stock boundaries. Rept. Int. Whal. Commn., Special Issue 13:39-68. 

Forney, K.A. 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994-2002. 

Admin. Rep. LJ-04-07. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92037. 17 pp. 

McDonald, M. A., and C. G. Fox. 1999. Passive acoustic methods applied to fin whale population density 

estimation. J. Acoust. Soc. Am. 105: 2643-2651. 

Mizroch, S. A., D. W. Rice, and J. M. Breiwick. 1984. The fin whale, Balaenoptera physalus Mar. Fish. Rev. 

46(4):20-24. 

Mobley, J. R., Jr., M. Smultea, T. Norris, and D. Weller. 1996. Fin whale sighting north of Kaua’i, Hawai’i. 

Pacific Science 50:230-233. 

273
Mobley, J. R., Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and 

abundance of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. 

Rep. LJ-00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 26 pp. 

Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

Northrop, J., W. C. Cummings, and P. O. Thompson. 1968. 20-Hz signals observed in the central Pacific. J. 

Acoust. Soc. Am. 43:383-384. 

Perrin, W.F., G. P. Donovan and J. Barlow. 1994. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Special Issue 

15, 629 pp. 

Richardson, W. J., C. R. Greene, Jr., C. I. Malme, and D. H. Thompson. 1995. Marine Mammals and Noise. 

Academic Press, San Diego. 576 p. 

Shallenberger, E.W. 1981. The status of Hawaiian cetaceans. Final report to U.S. Marine Mammal Commission. 

MMC-77/23, 79pp. 

Thompson, P. O. and W. A. Friedl. 1982. A long term study of low frequency sound from several species of whales 

off Oahu, Hawaii. Cetology 45:1-19. 

Tønnessen, J. N. and A. O. Johnsen. 1982. The History of Modern Whaling. Hurst, 789 pp. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

274
Revised 03/15/2005 

BRYDE'S WHALE (Balaenoptera edeni): Hawaiian Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE 

 Bryde's whales occur in tropical 

and warm temperate waters throughout 

the world. Shallenberger (1981) 

reported a sighting of a Bryde's whale 

southeast of Nihoa in April 1977 (see 

DeLong and Brownell 1977; 

Leatherwood et al. 1982: Fig. 39c). 

Leatherwood et al. (1982) described the 

species as relatively abundant in summer 

and fall on the Mellish and Miluoki 

banks northeast of Hawaii and around 

Midway Islands, but the basis for this 

statement was not explained. Ohsumi 

and Masaki (1975) reported the tagging 

of "many" Bryde's whales between the 

Bonin and Hawaiian Islands in the 

winters of 1971 and 1972 (Ohsumi 

1977). A summer/fall 2002 shipboard 

survey of waters within the U.S. 

Exclusive Economic Zone (EEZ) of the 

Hawaiian Islands resulted in 13 Bryde’s 

whale sightings throughout the study 

area (Figure 1; Barlow 2003).With 

presently available evidence, there is no 

biological basis for defining separate 

stocks of Bryde's whales in the central North Pacific. Bryde's whales also occasionally occur off southern California 

(Morejohn and Rice 1973). For the MMPA stock assessment reports, Bryde's whales within the Pacific U.S. EEZ 

are divided into two areas: 1) Hawaiian waters (this report), and 2) the eastern tropical Pacific (east of 150o

W and 

including the Gulf of California and waters off California). 

POPULATION SIZE

 Tillman (1978) concluded from Japanese and Soviet CPUE data that the stock size in the North Pacific 

pelagic whaling grounds, mostly to the west of the Hawaiian Islands, declined from approximately 22,500 in 1971 to 

17,800 in 1977. An estimate of 13,000 (CV=0.202) Bryde's whales was made from vessel surveys in the eastern 

tropical Pacific between 1986 and 1990 (Wade and Gerrodette 1993). The area to which this estimate applies is 

mainly east and somewhat south of the Hawaiian Islands, and it is not known whether these animals are part of the 

same population that occurs around the Hawaiian Islands. As part of the Marine Mammal Research Program of the 

Acoustic Thermometry of Ocean Climate (ATOC) study, a total of twelve aerial surveys were conducted within 

about 25 nmi of the main Hawaiian Islands in 1993, 1995 and 1998 (Mobley et al. 2000). No sightings of Bryde’s 

whales were made. A 2002 shipboard line-transect survey of the entire Hawaiian Islands EEZ resulted in an 

abundance estimate of 493 (CV=0.34) Bryde’s whales (Barlow 2003). This is currently the best available 

abundance estimate for this stock. 

Minimum Population Estimate

 The log-normal 20th percentile of the 2002 abundance estimate is 373 Bryde’s whales. 

 

Current Population Trend

 No data are available on current population trend. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

No data are available on current or maximum net productivity rate.

W180 W175 W170 W165 W160 W155 W150

N10

N15

N20

N25

N30

N35

Figure 1. Bryde’s whale sighting locations during the 2002 

shipboard survey of U.S. EEZ waters surrounding the Hawaiian 

Islands (Barlow 2003; see Appendix 2 for details on timing and 

location of survey effort). Outer line represents approximate 

boundary of survey area and U.S. EEZ. 

275
POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size 

(373) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.50 

(for a stock of unknown status with no known fishery mortality or serious injury within the Hawaiian Islands EEZ; 

Wade and Angliss 1997), resulting in a PBR of 3.7 Bryde’s whales per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY 

Fishery Information

 Information on fishery-related mortality of cetaceans in Hawaiian waters is limited, but the gear types used 

in Hawaiian fisheries are responsible for marine mammal mortality and serious injury in other fisheries throughout 

U.S. waters. Gillnets appear to capture marine mammals wherever they are used, and float lines from lobster traps 

and longlines can be expected to occasionally entangle whales (Perrin et al. 1994). Interactions with cetaceans are 

reported for all pelagic fisheries, and large whales have been entangled in longline gear off the Hawaiian Islands 

(Nitta and Henderson 1993, Forney 2004). Between 1994 and 2002, no interactions with Bryde’s whales were 

observed in the Hawaii-based longline fishery, with approximately 4-25% of all effort observed (Forney 2004). 

Historical Mortality

 Small numbers of Bryde's whales were taken near the Northwestern Hawaiian Islands by Japanese and 

Soviet whaling fleets during the early 1970s (Ohsumi 1977). Pelagic whaling for Bryde's whales in the North 

Pacific ended after the 1979 season (IWC 1981), and coastal whaling for this species ended in the western Pacific in 

1987 (IWC 1989).

STATUS OF STOCK

The status of Bryde's whales in Hawaiian waters relative to OSP is unknown, and there are insufficient data 

to evaluate trends in abundance. They are not listed as “threatened” or “endangered” under the Endangered Species 

Act (1973), nor as “depleted” under the MMPA. The Hawaiian stock of Bryde’s whale is not considered strategic 

under the 1994 amendments to the MMPA because there has been no reported fisheries related mortality or serious 

injury. Insufficient information is available to determine whether the total fishery mortality and serious injury for 

fin whales is insignificant and approaching zero mortality and serious injury rate. The increasing levels of 

anthropogenic noise in the world’s oceans has been suggested to be a habitat concern for whales (Richardson et al. 

1995). 

REFERENCES 

Barlow, J. 2003. Cetacean abundance in Hawaiian waters during summer/fall 2002. Admin. Rep. LJ-03-13. 

Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La 

Jolla, CA 92037. 

DeLong, R. L. and R. L. Brownell, Jr. 1977. Hawaiian monk seal (Monachus schauinslandi) habitat and population 

survey in the northwestern (Leeward) Hawaiian Islands, April 1977. Northwest Alaska Fish Cent. Proc. 

Rep., 43 pp. 

Forney, K.A. 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994-2002. 

Admin. Rep. LJ-04-07. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92037. 17 pp. 

International Whaling Commission. 1981. Japan. Progress report on cetacean research June 1979-May 1980. Rep. 

Int. Whal. Commn. 31:195-200. 

International Whaling Commission. 1989. Japan. Progress report on cetacean research June 1987 to April 1988. 

Rep. Int. Whal. Commn. 39:201-204. 

Leatherwood, S., R. R. Reeves, W. F. Perrin, and W. E. Evans. 1982. Whales, dolphins, and porpoises of the eastern 

North Pacific and adjacent arctic waters: A guide to their identification. NOAA Tech. Rep. NMFS 444, 

245 pp. 

Mobley, J. R. , Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and 

abundance of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. 

Rep. LJ-00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 26 pp. 

Morejohn, G. V. and D. W. Rice. 1973. First record of Bryde's whale (Balaenoptera edeni) off California. Cal. 

Fish Game 59:313-315. 

276
Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

Ohsumi, S. 1977. Stocks and trends of abundance of the sperm whale in the North Pacific. Rep. Int. Whal. Commn. 

27:167-175. 

Ohsumi, S. and Y. Masaki. 1975. Japanese whale marking in the North Pacific, 1963-72. Bull. Far Seas Fish. Res. 

Lab. 12:171-219. 

Perrin, W.F., G. P. Donovan and J. Barlow. 1994. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Special Issue 

15, 629 pp. 

Richardson, W. J., C. R. Greene, Jr., C. I. Malme, and D. H. Thompson. 1995. Marine Mammals and Noise. 

Academic Press, San Diego. 576 p. 

Shallenberger, E.W. 1981. The status of Hawaiian cetaceans. Final report to U.S. Marine Mammal Commission. 

MMC-77/23, 79pp. 

Tillman, M. F. 1978. Modified Delury estimates of the North Pacific Bryde's whale stock. Rep. Int. Whal. 

Commn. 28:315-317. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

Wade, P. R. and T. Gerrodette. 1993. Estimates of cetacean abundance and distribution in the eastern tropical 

Pacific. Rep. Int. Whal. Commn. 43:477-493. 

277
Revised 03/15/2005 

SEI WHALE (Balaenoptera borealis): Hawaiian Stock

STOCK DEFINITION AND GEOGRAPHIC RANGE

 The International Whaling 

Commission (IWC) only considers one 

stock of sei whales in the North Pacific 

(Donovan 1991), but some evidence 

exists for multiple populations (Masaki 

1977; Mizroch et al. 1984; Horwood 

1987). Sei whales are distributed far out 

to sea in temperate regions of the world 

and do not appear to be associated with 

coastal features. Whaling effort for this 

species was distributed continuously 

across the North Pacific between 45-

55oN (Masaki 1977). Two sei whales 

that were tagged off California were 

later killed off Washington and British 

Columbia (Rice 1974) and the 

movement of tagged animals has been 

noted in many other regions of the North 

Pacific. There is still insufficient 

information to accurately determine 

population structure, but from a 

conservation perspective it may be risky to 

assume panmixia in the entire North 

Pacific. Four sightings of sei whales were 

recently made during a summer/fall 2002 

shipboard survey of waters within the U.S. 

Exclusive Economic Zone (EEZ) of the Hawaiian Islands (Figure 1; Barlow 2003). For the Marine Mammal 

Protection Act (MMPA) stock assessment reports, sei whales within the Pacific U.S. EEZ are divided into three 

discrete, non-contiguous areas: 1) waters around Hawaii (this report), 2) California, Oregon and Washington waters, 

and 3) Alaskan waters. 

POPULATION SIZE

 Ohsumi and Wada (1974) estimate the pre-whaling abundance of sei whales to be 58,000-62,000 in the 

North Pacific. Later, Tillman (1977) used a variety of different methods to estimate the abundance of sei whales in 

the North Pacific and revised this pre-whaling estimate to 42,000. His estimates for the year 1974 ranged from 

7,260 to 12,620. All methods depend on using the history of catches and trends in CPUE or sighting rates; there 

have been no direct estimates of sei whale abundance in the entire North Pacific based on sighting surveys. As part 

of the Marine Mammal Research Program of the Acoustic Thermometry of Ocean Climate (ATOC) study, a total of 

twelve aerial surveys were conducted within about 25 nmi of the main Hawaiian Islands in 1993-98 (Mobley et al. 

2000), but no sightings of sei whales were made. A 2002 shipboard line-transect survey of the entire Hawaiian 

Islands EEZ resulted in a summer/fall abundance estimate of 77 (CV=1.06) sei whales (Barlow 2003). This is 

currently the best available abundance estimate for this stock, but the majority of sei whales would be expected to be 

at higher latitudes in their feeding grounds at this time of year. 

Minimum Population Estimate

 The log-normal 20th percentile of the 2002 abundance estimate is 37 sei whales. 

Current Population Trend

 No data are available on current population trend. Although the population in the North Pacific is expected 

to have grown since being given protected status in 1976, the possible effects of continued unauthorized takes 

(Yablokov 1994) make this uncertain. 

W180 W175 W170 W165 W160 W155 W150

N10

N15

N20

N25

N30

N35

Figure 1. Sei whale sighting locations during the 2002 shipboard 

cetacean survey of U.S. EEZ waters surrounding the Hawaiian 

Islands (Barlow 2003; see Appendix 2 for details on timing and 

location of survey effort). Outer line indicates approximate 

boundary of survey area and U.S. EEZ. 

278
CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No data are available on current or maximum net productivity rate for sei whales. 

POTENTIAL BIOLOGICAL REMOVAL

 The potential biological removal (PBR) level for this stock is calculated as the minimum population size 

(37) times one half the default maximum net growth rate for cetaceans (1⁄2 of 4%) times a recovery factor of 0.1 (the 

default value for an endangered species; Wade and Angliss 1997), resulting in a PBR of 0.1 sei whales per year. 

HUMAN-CAUSED MORTALITY AND SERIOUS INJURY

Fishery Information 

 Information on fishery-related mortality of cetaceans in Hawaiian waters is limited, but the gear types used 

in Hawaiian fisheries are responsible for marine mammal mortality and serious injury in other fisheries throughout 

U.S. waters. Gillnets appear to capture marine mammals wherever they are used, and float lines from lobster traps 

and longlines can be expected to occasionally entangle whales (Perrin et al. 1994). Interactions with cetaceans are 

reported for all pelagic fisheries, and large whales have been entangled in longline gear off the Hawaiian Islands 

(Nitta and Henderson 1993; Forney 2004). Between 1994 and 2002, no interactions with sei whales were observed 

in the Hawaii-based longline fishery, with approximately 4-25% of all effort observed (Forney 2004). 

Historical Whaling

 The reported take of North Pacific sei whales by commercial whalers totaled 61,500 between 1947 and 

1987 (C. Allison, IWC, pers. comm.). There has been an IWC prohibition on taking sei whales since 1976, and 

commercial whaling in the U.S. has been prohibited since 1972. 

STATUS OF STOCK 

Previously, sei whales were estimated to have been reduced to 20% (8,600 out of 42,000) of their prewhaling abundance in the North Pacific (Tillman 1977). Sei whales are formally listed as "endangered" under the 

Endangered Species Act (ESA), and consequently the Hawaiian stock is automatically considered as a "depleted" 

and "strategic" stock under the MMPA. Insufficient information is available to determine whether the total fishery 

mortality and serious injury for sei whales is insignificant and approaching zero mortality and serious injury rate. 

The increasing levels of anthropogenic noise in the world’s oceans has been suggested to be a habitat concern for 

whales (Richardson et al. 1995). 

REFERENCES

Allison, C. International Whaling Commission. The Red House, 135 Station Road, Impington, Cambridge, UK CB4 

9NP. 

Barlow, J. 2003. Cetacean abundance in Hawaiian waters during summer/fall 2002. Admin. Rep. LJ-03-13. 

Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La 

Jolla, CA 92038. 

Donovan, G. P. 1991. A review of IWC stock boundaries. Rept. Int. Whal. Commn., Special Issue 13:39-68. 

Forney, K.A. 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994-2002. 

Admin. Rep. LJ-04-07. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92037. 17 pp. 

Horwood, J. 1987. The Sei Whale: Population Biology, Ecology and Management. Croom Helm, London, U.K. 

375pp. 

Masaki, Y. 1977. The separation of the stock units of sei whales in the North Pacific. Rept. Int. Whal. Commn., 

Special Issue 1:71-77. 

Mizroch, S. A., D. W. Rice, and J. M. Breiwick. 1984. The sei whale, Balaenoptera borealis. Mar. Fish. Rev. 

46:25-29. 

Mobley, J. R., Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and 

abundance of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. 

Rep. LJ-00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La 

Jolla, CA 92038. 26 pp. 

Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

279
Ohsumi, S. and S. Wada. 1974. Status of whale stocks in the North Pacific, 1972. Rept. Int. Whal. Commn. 

25:114-126. 

Perrin, W.F., G. P. Donovan and J. Barlow. 1994. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Special Issue 

15, 629 pp. 

Rice, D. W. 1974. Whales and whale research in the eastern North Pacific. pp. 170-195 In: W. E. Schevill (ed.). 

The Whale Problem: A Status Report. Harvard Press, Cambridge, MA. 

Richardson, W. J., C. R. Greene, Jr., C. I. Malme, and D. H. Thompson. 1995. Marine Mammals and Noise. 

Academic Press, San Diego. 576 p. 

Tillman, M. F. 1977. Estimates of population size for the North Pacific sei whale. Rept. Int. Whal. Commn., 

Special Issue 1:98-106. 

Yablokov, A. V. 1994. Validity of whaling data. Nature 367:108. 

Wade, P. R. and R. P. Angliss. 1997. Guidelines for Assessing Marine Mammal Stocks: Report of the GAMMS 

Workshop April 3-5, 1996, Seattle, Washington. U. S. Dep. Commer., NOAA Tech. Memo. NMFS-OPR12. 93 pp. 

280
Revised 03/15/2005

MINKE WHALE (Balaenoptera acutorostrata): Hawaiian Stock 

STOCK DEFINITION AND GEOGRAPHIC RANGE

 The International Whaling 

Commission (IWC) recognizes 3 stocks 

of minke whales in the North Pacific: one 

in the Sea of Japan/East China Sea, one 

in the rest of the western Pacific west of 

180oN, and one in the "remainder" of the 

Pacific (Donovan 1991). The 

"remainder" stock only reflects the lack 

of exploitation in the eastern Pacific and 

does not imply that only one population 

exists in that area (Donovan 1991). In the 

"remainder" area, minke whales are 

relatively common in the Bering and 

Chukchi seas and in the Gulf of Alaska, 

but are not considered abundant in any 

other part of the eastern Pacific 

(Leatherwood et al. 1982; Brueggeman et 

al. 1990). In the Pacific, minke whales 

are usually seen over continental shelves 

(Brueggeman et al. 1990). In the extreme 

north, minke whales are believed to be 

migratory, but in inland waters of 

Washington and in central California 

they appear to establish home ranges 

(Dorsey et al. 1990). 

 Minke whales have only been 

recently confirmed to occur seasonally 

around the Hawaiian Islands (Barlow 2003, 

Rankin and Barlow, in prep), and their 

migration routes or destinations are not 

known. Four reliable sightings of minke 

whales were made by observers in the 

Hawaii-based longline fishery during the 

months of December-March, 2000-2002 

(Figure 1; NMFS/PIR unpublished data). One confirmed sighting of a minke whale was made in November 2002 

during a survey of waters within the U.S. Exclusive Economic Zone (EEZ) of the Hawaiian Islands (Barlow 2003), 

and additional acoustic detections of this species’ distinctive call (known as the ‘boing’) were made that could not 

be visually verified (Figure 1). There are no known stranding records of this species from the main islands (Nitta 

1991; Maldini 2005). For the Marine Mammal Protection Act (MMPA) stock assessment reports, there are three 

stocks of minke whale within the Pacific U.S. EEZ: 1) a Hawaiian stock (this report), 2) a California/Oregon/ 

Washington stock, and 3) an Alaskan stock. 

POPULATION SIZE

 A summer/fall 2002 shipboard line-transect survey of the entire Hawaiian Islands EEZ resulted in one ‘off 

effort’ sighting of a minke whale following the acoustic detection of a so-called ‘boing’ (Barlow 2003; Rankin and 

Barlow, in prep). This sighting was not part of regular survey operations and, therefore, could not be used to 

calculate an estimate of abundance (Barlow 2003). Furthermore, the majority of this survey took place during 

summer and early fall, when the Hawaiian stock of minke whale would be expected to be farther north. There 

currently is no abundance estimate for this stock of minke whales, which appears to occur seasonally (about 

November - March) around the Hawaiian Islands. 

Figure 1. Locations of minke whale sightings from longline 

observer records (diamonds; NMFS/PIR, unpublished data), and 

sighting (closed circle) and acoustic detections (open circles) 

made during the 2002 shipboard survey of U.S. EEZ waters 

surrounding the Hawaiian Islands (Barlow 2003; see Appendix 2 

for details on timing and location of survey effort). Solid lines 

represent the U.S. EEZ. 

281
Minimum Population Estimate

 There is no minimum population estimate for the Hawaiian stock of minke whales. 

Current Population Trend

 No data are available on current population trend. 

CURRENT AND MAXIMUM NET PRODUCTIVITY RATES

 No data are available on current or maximum net productivity rate for Hawaiian minke whales. 

POTENTIAL BIOLOGICAL REMOVAL

 No PBR can be calculated for this stock at this time. 

HUMAN CAUSED MORTALITY AND SERIOUS INJURY 

Fishery Information

 Information on fishery-related mortality and serious injury of cetaceans in Hawaiian waters is limited, but 

the gear types used in Hawaiian fisheries are responsible for marine mammal mortality and serious injury in other 

fisheries throughout U.S. waters. Gillnets appear to capture marine mammals wherever they are used, and float lines 

from lobster traps and longlines can be expected to occasionally entangle whales (Perrin et al. 1994). Interactions 

with cetaceans have been reported for all Hawaiian pelagic fisheries (Nitta and Henderson 1993), but none of these 

interactions are known to have involved minke whales. None were observed hooked or entangled in the Hawaiibased longline fishery between 1994 and 2002, with approximately 4-25% of all effort (measured as the number of 

sets made) observed by on-board observers (Forney 2004). 

STATUS OF STOCK

 The status of minke whales in Hawaiian waters relative to OSP is unknown, and there are insufficient data 

to evaluate trends in abundance. They are not listed as “threatened” or “endangered” under the Endangered Species 

Act (1973), nor as “depleted” under the MMPA. Although information on minke whales in Hawaiian waters is 

limited, this stock would not be considered strategic under the 1994 amendments to the MMPA because there has 

been no reported fisheries related mortality or serious injury within the Hawaiian Islands EEZ. Insufficient 

information is available to determine whether the total fishery mortality and serious injury for minke whales is 

insignificant and approaching zero mortality and serious injury rate. The increasing levels of anthropogenic noise in 

the world’s oceans has been suggested to be a habitat concern for whales (Richardson et al. 1995). 

REFERENCES

Barlow, J. 2003. Cetacean abundance in Hawaiian waters during summer/fall 2002. Admin. Rep. LJ-03-13. 

Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La Jolla Shores Drive, La 

Jolla, CA 92037. 

Brueggeman, J. J., G. A. Green, K. C. Balcomb, C. E. Bowlby, R. A. Grotefendt, K. T. Briggs, M. L. Bonnell, R. G. 

Ford, D. H. Varoujean, D. Heinemann, and D. G. Chapman. 1990. Oregon-Washington Marine Mammal 

and Seabird Survey: Information synthesis and hypothesis formulation. U.S. Department of the Interior, 

OCS Study MMS 89-0030. 

Donovan, G. P. 1991. A review of IWC stock boundaries. Rept. Int. Whal. Commn., Special Issue 13:39-68. 

Dorsey, E. M., S. J. Stern, A. R. Hoelzel, and J. Jacobsen. 1990. Minke whale (Balaenoptera acutorostrata) from 

the west coast of North America: individual recognition and small-scale site fidelity. Rept. Int. Whal. 

Commn., Special Issue 12:357-368. 

Leatherwood, S., R. R. Reeves, W. F. Perrin, and W. E. Evans. 1982. Whales, dolphins, and porpoises of the 

eastern North Pacific and adjacent Arctic waters: A guide to their identification. NOAA Technical Rept. 

NMFS Circular 444. 245pp. 

Forney, K.A. 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994-2002. 

Admin. Rep. LJ-04-07. Southwest Fisheries Science Center, National Marine Fisheries Service, 8604 La 

Jolla Shores Drive, La Jolla, CA 92037. 17 pp. 

Maldini, D., L. Mazzuca, and S. Atkinson. 2005. Odontocete stranding patterns in the Main Hawaiian Islands 

(1937-2002): How do they compare with live animal surveys? Pacific Science 59(1):55-67. 

NMFS, Pacific Islands Region, Observer Program, 1602 Kapiolani Blvd, Suite 1110, Honolulu, HI 96814. 

Nitta, E. 1991. The marine mammal stranding network for Hawaii: an overview. In: J.E. Reynolds III, D.K. Odell 

(eds.), Marine Mammal Strandings in the United States, pp.56-62. NOAA Tech. Rep. NMFS 98, 157 pp. 

282
Nitta, E. and J. R. Henderson. 1993. A review of interactions between Hawaii's fisheries and protected species. 

Mar. Fish. Rev. 55(2):83-92. 

Perrin, W. F., G. P. Donovan and J. Barlow. 1994. Gillnets and Cetaceans. Rep. Int. Whal. Commn., Spec. Issue 15, 

629p. 

Rankin, S. and J. Barlow. (in prep). Description of stereotyped minke whale vocalizations from the North Pacific 

Ocean. 

Richardson, W. J., C. R. Greene, Jr., C. I. Malme, and D. H. Thompson. 1995. Marine Mammals and Noise. 

Academic Press, San Diego. 576 p. 

283
Revised 05/15/2006 Appendix 1. Description of U.S. Commercial Fisheries 

The Marine Mammal Protection Act (MMPA) requires NMFS to publish a list of commercial fisheries (List Of 

Fisheries or “LOF”) and classify each fishery based on whether incidental mortality and serious injury of marine mammals 

is frequent (Category I), occasional (Category II), or unlikely or unknown (Category III). The LOF is published annually in 

the Federal Register. The categorization of a fishery in the LOF determines whether participants in that fishery are subject 

to certain provisions of the MMPA, such as registration, observer coverage, and take reduction plan requirements. The 

categorization criteria as they appear in the LOF is reprinted below: 

 The fishery classification criteria consist of a two-tiered, stock-specific approach that first addresses the total impact 

of all fisheries on each marine mammal stock, and then addresses the impact of individual fisheries on each stock. This 

approach is based on consideration of the rate, in numbers of animals per year, of incidental mortalities and serious injuries 

of marine mammals due to commercial fishing operations relative to the Potential Biological Removal (PBR) level for each 

marine mammal stock. The MMPA (16 U.S.C. 1362 (20)) defines the PBR level as the maximum number of animals, not 

including natural mortalities, that may be removed from a marine mammal stock while allowing that stock to reach or 

maintain its optimum sustainable population. This definition can also be found in the implementing regulations for section 

118 at 50 CFR 229.2. 

 Tier 1: If the total annual mortality and serious injury across all fisheries that interact with a stock is less than or 

equal to 10 percent of the PBR level of the stock, all fisheries interacting with the stock would be placed in Category III. 

Otherwise, these fisheries are subject to the next tier (Tier 2) of analysis to determine their classification. 

 Tier 2, Category I: Annual mortality and serious injury of a stock in a given fishery is greater than or equal to 50 

percent of the PBR level. 

 Tier 2, Category II: Annual mortality and serious injury of a stock in a given fishery is greater than 1 percent and 

less than 50 percent of the PBR level. 

 Tier 2, Category III: Annual mortality and serious injury of a stock in a given fishery is less than or equal to 1 

percent of the PBR level. 

While Tier 1 considers the cumulative fishery mortality and serious injury for a particular stock, Tier 2 considers fisheryspecific mortality and serious injury for a particular stock. Additional details regarding how the categories were determined 

are provided in the preamble to the final rule implementing section 118 of the MMPA (60 FR 45086, August 30, 1995). 

Since fisheries are categorized on a per-stock basis, a fishery may qualify as one Category for one marine mammal stock 

and another Category for a different marine mammal stock. A fishery is typically categorized on the LOF at its highest level 

of classification (e.g., a fishery that qualifies for Category III for one marine mammal stock and for Category II for another 

marine mammal stock will be listed under Category II). 

Other Criteria That May Be Considered

 In the absence of reliable information indicating the frequency of incidental mortality and serious injury of marine 

mammals by a commercial fishery, NMFS will determine whether the incidental serious injury or mortality qualifies for 

Category II by evaluating other factors such as fishing techniques, gear used, methods used to deter marine mammals, 

target species, seasons and areas fished, qualitative data from logbooks or fisher reports, stranding data, and the species and

distribution of marine mammals in the area, or at the discretion of the Assistant Administrator for Fisheries (50 CFR 229.2). 

This appendix describes commercial fisheries that occur in California, Oregon, Washington, and Hawaiian waters and that 

interact or may interact with marine mammals. The first three sections describe sources of marine mammal mortality data 

for these fisheries. The fourth section describes the commercial fisheries for these states. A list of all known fisheries for 

these states was published as a proposed rule in the Federal Register, 71 FR 20941, 24 April 2006. 

1. Sources of Mortality/Injury Data

 There are three major sources of marine mammal mortality/injury data for the active commercial fisheries in 

California, Oregon, and Washington. These sources are the NMFS Observer Programs, the Marine Mammal Authorization 

284
Revised 05/15/2006 Appendix 1. Description of U.S. Commercial Fisheries 

Program (MMAP) data, and the NMFS Marine Mammal Stranding Network (MMSN) data. Each of these data sources has 

a unique objective. Data on mammal mortality and injury are reported to the MMAP by fishers in any commercial 

fisheries. Marine mammal mortality and injury is also monitored by the NMFS Marine Mammal Stranding Network 

(MMSN). Data provided by the MMSN is not duplicated by either the NMFS Observer Program or MMAP reporting. 

Human-related data from the MMSN include occurrences of mortality due to entrainment in power station intakes, ship 

strikes, shooting, evidence of net fishery entanglement (net remaining on animal, net marks, severed flukes), and ingestion 

of hooks. 

2. Marine Mammal Reporting from Fisheries 

 In 1994, the MMPA was amended to implement a long-term regime for managing mammal interactions with 

commercial fisheries (the Marine Mammal Authorization Program, or MMAP). Logbooks are no longer required - instead 

vessel owners/operators in any commercial fishery (Category I, II, or III) are required to submit one-page pre-printed 

reports for all interactions (including those that occur while an observer is onboard) resulting in an injury or mortality to a 

marine mammal. The report must include owner/operator’s name and address, vessel name and ID, where and when the 

interaction occurred, the fishery, species involved, and type of injury (if the animal was released alive). These postage-paid

report forms are mailed to all Category I and II fishery participants that have registered with NMFS, and must be completed 

and returned to NMFS within 48 hours of returning to port for trips in which a marine mammal injury or mortality 

occurred. The number of self-reported marine mammal interactions is considerably lower than the number reported by 

fishery observers, even though observer reports are typically based on 20% observer effort. For example, from 2000-2004, 

there were 112 fisher self-reports of marine mammal interactions in the California swordfish/thresher shark drift gillnet 

fishery. This compares with 141 observed interactions over the same period, based on only 20% observer coverage. This 

suggests that fisher self-reports are grossly underreported. A summary comparing fisher self-reports and observer reports 

of marine mammal interactions for the swordfish drift gillnet fishery is given in Table 1 of this Appendix. 

3. NMFS Marine Mammal Stranding Network data

 From 2000-2004, there were 1,022 cetacean and 13,215 pinniped strandings recorded in California, Oregon, and 

Washington states. Approximately 10% of all cetacean and 6% of all pinniped strandings showed evidence of humancaused mortality during this period. Human-related causes of mortality include: entrainment in power station intakes, 

shooting, net fishery entanglement, and hook/line, set-net and trap fishery interaction. A species summary of all cetacean 

and pinniped strandings for the period 2000-2004 is given in Table 2 of this Appendix. 

4. Fishery Descriptions

Category I, CA/OR thresher shark/swordfish drift gillnet fishery (≥14 inch mesh)

Note: NMFS has proposed reclassifying this fishery to a Category I, based on a revised PBR level for short-finned pilot 

whales and an observed take of a short-finned pilot whale in this fishery in 2003 (Federal Register 69 FR 70094, 02 

December 2004). 

Number of permit holders: The number of eligible permit holders in California for 2000-2004 are 127, 114, 106, 99, and 

96 respectively. Permits are non-transferable and are linked to individual fishermen, not vessels. 

Number of active permit holders: The number of vessels active in this fishery from 2000-2004 were 78, 69, 50, , 43, and 

43 respectively. Information on the number of permit holders is obtained from the Status of the U.S. west coast fisheries 

for Highly Migratory Species through 2004; Stock Assessment and Fishery Evaluation report available from the Pacific 

Fishery Management Council website (www.pcouncil.org). 

Total effort: Both estimated and observed effort for the drift-net fishery during the calendar years 1990 through 2002 are 

shown in Figure 7. In 2004 there was an estimated 1,084 effort-days, where an effort-day is defined to be one day of effort 

by one vessel. (In this fishery, 1 effort-day is equivalent to 1 set.). There were 223 (41 trips) observed effort-days in 2004. 

An estimated 1,075 sets were fished in 2005, of which 225 sets were observed from 44 vessel trips, for an observer 

coverage rate of 21%. In 2005, 40 vessels were active in this fishery, though only 27 were observed. Seven vessels 

considered ‘observable’ were not observed and reported fishing 79 sets. Reasons given for not being observed included 

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limited fishing effort, mechanical problems, and extra crewmembers. Six vessels that reported a total of 111 sets were 

considered ‘unobservable’ because they lacked berthing space for an observer. 

Geographic range: Effort in this fishery ranges from the U.S./Mexico border north to waters off the state of Oregon. For 

this fishery there are area-season closures (see below). Figures 1-5 show locations of observed sets and Figure 6 shows 

approximate locations of observed marine mammal entanglements for the period 1998-2002. 

Seasons: This fishery is subject to season-area restrictions. From February 1 to May 15 effort must be further than 200 

nautical miles (nmi) from shore; from May 16 to August 14, effort must be further than 75 nmi from shore, and from 

August 15 to January 31 there is only the 3 nmi off-shore restriction for all gillnets in southern California (see angel 

shark/halibut fishery below). The majority of the effort occurs from October through December. A season-area closure to 

protect leatherback sea turtles was implemented in this fishery in August 2001. The closure area prohibits drift gillnet 

fishing from August 15 through November 15, in the area bounded by straight lines from Point Sur, California (N36o 17') to 

N 34o 27' W 123o

 35', west to W129o, north to N 45o, then east to the Oregon coast. In March 2006, the Pacific Fishery 

Management Council approved a recommendation to NMFS to reopen the current closure area under an exempted fishing 

permit (EFP). The EFP requires 100% observer coverage and limits the number of sets fished to 300. Additionally, fishing 

in the area would cease prior to the 300 set limit if 2 leatherback turtles are entangled. In addition, fishing would cease if

one mortality or serious injury is documented for any of the following species: gray whale, short-finned pilot whale, sperm 

whale, fin whale, humpback whale, and minke whale. NMFS may modify this recommendation and will make a final 

decision on the EFP in 2006. An additional season-area closure south of Point Conception and east of W120 degrees 

longitude is effective during the months of June, July, and August during El Niño years to protect loggerhead turtles 

(Federal Register, 68 FR 69962, 16 December 2003). 

Gear type and fishing method: Typical gear used for this fishery is a 1000 fathom gillnet with a stretched mesh size 

typically ranging from 18-22 inches (14 inch minimum). The net is set at dusk and allowed to drift during the night after 

which, it is retrieved. The fishing vessel is typically attached to one end of the net. Soak duration is typically 12-14 hours 

depending on the length of the night. Net extender lengths of a minimum 36 ft. became mandatory for the 1997-1998 

fishing season. The use of acoustic warning devices (pingers) became mandatory 28 October 1997. 

Regulations: The fishery is managed under a Fishery Management Plan (FMP) developed by the Pacific Fishery 

Management Council and NMFS. 

Management type: The drift-net fishery is a limited entry fishery with seasonal closures and gear restrictions (see above). 

The state of Oregon restricts landing to swordfish only. 

Comments: This fishery has had a NMFS observer program in place since July 1990. Due to bycatch of strategic stocks 

including short-finned pilot whale, beaked whales, sperm whale and humpback whale, a Take Reduction Team was formed 

in 1996. Since then, the implementation of increased extender lengths and the deployment of pingers have substantially 

decreased cetacean entanglement. The fraction of active vessels in this fishery that are not observed owing to a lack of 

berthing space for observers has been increasing as larger vessels drop out of this fishery. 

Category I, CA angel shark/halibut and other species set gillnet fishery (>3.5 inch mesh).

Note: The “CA angel shark/halibut set gillnet fishery” and “CA other species, large mesh (>3.5 in) set gillnet fishery” 

were previously listed as separate fisheries. Angel shark and halibut are typically targeted using 8.5 inch mesh while the 

remainder of the fishery targets white seabass and yellowtail using 6.5 inch mesh. In recent years, there has been an 

increasing number of 6.0-6.5 inch mesh sets fished using drifting methods; this component is now identified as a separate 

fishery (see “CA yellowtail, barracuda, white seabass, and tuna drift gillnet fishery (>3.5 and <14 in mesh)” fishery 

described below). 

Number of permit holders: There is no specific permit category for this fishery. Overall, the current number of legal 

permit holders for gill and trammel nets, excluding swordfish drift gillnets and herring gillnets for 2000-2004 are, 

respectively, 232, 223, 209, 193, and 187. Information on permit numbers is available from the California Department of 

Fish and Game website (http://www.dfg.ca.gov/licensing). 

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Number of active permit holders: Based on logbook data, there were at least 41 active permit holders from April 2003 to 

April 2004. 

Total effort: From 1999-2003, estimated fishing effort (from logbooks) in this fishery has been 4,173, 3,736, 3,388, 

3,220, and 2,788 days, respectively. A summary of estimated fishing effort and observer coverage for the years 1990-2003 

is shown in Figure 8. Effort in the white seabass and yellowtail portion of this fishery from 1999-2003 were 460, 657, 551, 

733 and 789 days, respectively. A portion of the effort in the white seabass and yellowtail fishery utilizes drifting nets (see 

“CA yellowtail, barracuda, white seabass, and tuna drift gillnet fishery (>3.5 and <14 in mesh)” fishery description below). 

Geographic range: Effort in this fishery previously ranged from the U.S./Mexico border north to Monterey Bay and was 

localized in more productive areas: San Ysidro, San Diego, Oceanside, Newport, San Pedro, Ventura, Santa Barbara, Morro 

Bay, and Monterey Bay. Fishery effort is now predominantly in the Ventura Flats area off of Ventura, the San Pedro area 

between Pt. Vicente and Santa Catalina Island and in the Monterey Bay area. The central California portion of the fishery 

from Point Arguello to Point Reyes has been closed since September 2002 when a ban on gillnets inshore of 60 fathoms 

took effect. 

Seasons: This fishery operates year round. Effort generally increases during the summer months and declines during the 

last three months of a year. 

Gear type and fishing method: Typical gear used for this fishery is a 200 fathom gillnet with a stretched mesh size of 8.5 

inches. The component of this fishery that targets white seabass and yellowtail utilizes 6.5 inch mesh. The net is generally 

set during the day and allowed to soak for up to 2 days. Soak duration is typically 8-10, 19-24, or 44-49 hours. The depth 

of water ranges from 15-50 fathoms with most sets in water depths of 15-35 fathoms. 

Regulations: This fishery is managed by the California Dept. of Fish and Game in accordance with state and federal laws. 

Management type: The halibut/angel shark set-net fishery is a limited entry fishery with gear restrictions and area closures. 

Comments: An observer program for the halibut/angel shark portion of this fishery operated from 1990-94 and was 

discontinued after area closures were implemented in 1994, which prohibited gillnets within 3 nmi of the mainland and 

within 1 nmi of the Channel Islands in southern California. NMFS re-established an observer program for this fishery in 

Monterey Bay in 1999-2000 due to a suspected increase in harbor porpoise mortality in Monterey Bay. In 1999 and 2000, 

fishery mortality exceeded PBR for the Monterey Bay harbor porpoise stock, and the stock is currently designated as 

strategic. In the autumn of 2000, the California Department of Fish and Game implemented the first in a series of 

emergency area closures to set gillnets within 60 fathoms along the central California coast. This effectively reduced 

fishing effort to negligible levels in 2001 and 2002 in Monterey Bay. A ban on gill and trammel nets inside of 60 fathoms 

from Point Reyes to Point Arguello became effective in September 2002. Mortality of marine mammals continues in this 

fishery, as evidenced by fisher self-reports under the Marine Mammal Authorization Program (MMAP) from 2000-2005. 

During this time, fishermen reported mortalities totalling 60 California sea lions, 20 harbor seals, one northern elephant seal

and one unidentified common dolphin. NMFS plans on reinitiating some level of observer coverage in this fishery in 2006. 

Category I, Hawaii swordfish, tuna, billfish, mahi mahi, wahoo, and oceanic shark longline/set line fishery.1

Note: The classification of this fishery was elevated to Category I in 2004 based on revised PBR levels of false killer 

whales and observed false killer whale mortalities in this fishery (Federal Register 69 FR 48407 1, 10 August 2004). 

Number of permit holders: The number of Hawaii longline limited access permit holders is 164. Not all such permits are 

renewed and used every year (approximately 126 were renewed in 2003). Most holders of Hawaii longline limited access 

permits are based in, or operate out of, Hawaii. Longline general permits are not limited by number. Approximately 67 

longline general permits were issued in 2003, about 48 of which were active. In 2003 all but two holders of longline general 

 

1

 This fishery description was provided in part by Chris Yates (NMFS) and from published fishery regulations in the 

Federal Register; 69 FR 48407, published 10 August 2004. 

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permits were based in, or operated out of, American Samoa. The remaining two, neither of which was active in 2003, were 

based in the Mariana Islands (Federal Register 69 FR 17329, 2 April 2004). 

Number of active permit holders: From 1998-2002 there were 115, 122, 125, 101, and 102 vessels actively fishing, 

respectively. There were 126 permits renewed in 2003 (Federal Register 69 FR 17329, 2 April 2004). In 2004, there were 

125 Hawaii longline limited access permits renewed, with 119 active. In 2004, there were 40 active permits in American 

Samoa. 

Total effort: For the years 1998-2002, there were 1,181, 1,165, 1,135, 1,075, and 1,193 trips made respectively. The 

number of hooks set has steadily increased since 1997 (15.5 million) and peaked in 2002 with 27 million hooks set. In 

2002, most effort occurred within the U.S. EEZ (approximately 15 million hooks set), while 12 million hooks were set 

outside the U.S. EEZ. At Kingman Reef and Palmyra Atoll there were 2.1 million hooks set in 2002. In 2003, there were 

1,214 trips recorded (with tuna as the target species). There were a total of 29.8 million hooks set in 2003, of these, 15 

million occurred outside the U.S. EEZ, 11 million within the Main Hawaiian Islands EEZ, 2.7 million within the Northwest 

Hawaiian Islands EEZ, and the remaining 0.9 million within other U.S. possession EEZs. The preliminary estimate of 

hooks fished in 2004 is 32 million hooks. 2003 logbook data for American Samoa consisted of 932 trips by 51 vessels, 

which made 6,220 sets, with 14.2 million hooks fished. Preliminary logbook data from 2004 in American Samoa consists 

of 623 trips by 40 vessels, which made 4,804 sets, with 11.6 million hooks fished. 

Geographic range: This fishery encompasses a huge geographic range extending North-South from 40° N to the equator 

and East-West from Kure Atoll to as far as 135° W. Fishing for swordfish generally occurs north of Hawaii, (as much as 

2,000 miles from Honolulu), whereas fishing for tunas occurs around the Main Hawaiian Islands (MHI) and south of the 

Hawaiian Islands. New regulations published in 2004 lift previous area closures north of the equator. 

Seasons: This fishery operates year-round. Effort is generally lower in the third quarter of the year. 

Gear type: The basic unit of gear is the main line which is made of monofilament and stored on a large hydraulic reel. 

Eight hundred to 1000 hooks are attached to 30 to 40 miles of main line on a typical fishing day. Shallow sets for 

swordfish and deep sets for tuna are fished with a requirement that the fishermen must declare prior to departure which set 

type will be employed. (There was no Hawaii-based shallow set swordfish fishery from 2001-2003). All shallow 

swordfish sets are required to utilize size 18/0 circle hooks with a 10 degree offset and mackerel bait (the use of squid bait 

is prohibited). Deployment and retrieval of gear must occur at night. For deep sets, all float lines must be at least 20 

meters in length; with a minimum of 15 branch lines between any two floats (except basket-style longline gear which may 

have as few as 10 branch lines between any two floats); without the use of light sticks; and resulting in the possession or 

landing of no more than 10 swordfish (Xiphias gladius) at any time during a given trip. As used in this definition “float 

line” means a line used to suspend the main longline beneath a float and ``light stick'' means any type of light emitting 

device, including any fluorescent “glow bead”, chemical, or electrically powered light that is affixed underwater to the 

longline gear . There are currently no Hawaii longline vessels deploying basket gear. 

 While similar, swordfish and tuna gear differ in the depth at which it is deployed, the number of hooks deployed, 

and the time of day at which it is set. Both styles use a monofilament mainline that is generally 3.2- 4.0 mm in diameter 

that is stored, deployed, and retrieved using a large hydraulic reel (some vessels may have two). In general, swordfish gear 

is deployed at an average depth (deepest) of 70m, with 600-1000 hooks deployed per day (3-6 hooks between floats), and 

the line is set at night and hauled during daylight hours. Additionally, float lines are usually less than the required twenty

meters (~10m) for tuna fishing. Because some swordfish vessels carry two reels of mainline, it is not uncommon for 

swordfish vessels to set as much as 60 miles of line in a day. In contrast, tuna gear is set much deeper (~200m), with 1500-

2200 hooks deployed per day (20-35 hooks between floats), the line is set in the morning and hauled in the evening. In 

addition, tuna mainline is deployed using a hydraulic line shooter. Regulations permit a minimum of 15 hooks between 

floats. There is no minimum for trips targeting swordfish. The line shooter sends the line off the vessel faster than the 

vessel is moving creating deep arcing caternaries in the line. This allows them to target deep dwelling tunas. Swordfish 

mainline is set at the same speed as the vessel to keep the line in shallower depths. Finally, lightsticks are prohibited during 

tuna (deep set) fishing operations. These are allowed in the swordfish fishery. 

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 The leaders attached to the mainline also differ between the two fisheries. A tuna leader is usually comprised of a 

hook immediately followed by a length of wire (1-2 mm thick) which is attached to a weighted swivel. The rest of the tuna 

leader in comprised of ~2mm thick monofilament and a snap for attachment to the mainline. The swordfish gear is 

comprised of a 18/0 or larger circle hook attached to a ~ 10m length of ~2mm monofilament line to a weighted swivel 

followed by another ~10m length of ~2mm monofilament. All attachments are made using loops secured by crimps. 

 Vessel operators are required to call NMFS for possible observer placement 72 hours prior to departure. At that 

time they must declare if they intend to go on a shallow-set or deep-set fishing trip. Regulations prohibiting the presence of

lightsticks and float lines shorter than 20m aboard vessels on declared deep-set trips preclude fishermen from fishing trip 

types while at sea - additionally a vessel returning from a deep-set trip cannot land more than 10 swordfish (50 CFR 

660.22). 

 Additional requirements for sea birds went into effect 18 January 2006 for vessels fishing above 23 degrees north 

latitude (Federal Register 70 FR 75075, 19 December 2005). Fishermen will be given a choice between side setting and 

employing a suite of seabird mitigation measures. Currently, regulations require deep-setting vessels to dye their bait blue, 

thoroughly thaw the bait, and throw all offal on the opposite side of the vessel from which fishing operations are taking 

place. (There have been no observations of marine mammals feeding on offal discarded from Hawaii-based longline 

vessels.) Additionally, these vessels are required to use a line shooter – which they would have anyway – and at least fortyfive gram weights on the line. 

Regulations: Effort is required to be outside of 50 nautical miles from the entire Northwestern Hawaiian islands (NWHI) 

because of possible protected species (monk seal) interactions. Several closed areas 25 to 75 nautical miles in radius also 

exist around the MHI to prevent gear conflicts with smaller fishing vessels. Current regulations require 100% observer 

coverage for shallow swordfish sets and 20% observer coverage for deep tuna sets. There are fleet-wide annual limits on 

the number of allowable sea turtle interactions in this fishery (16 leatherbacks or 17 loggerheads). The shallow set 

component of the fishery is closed if either threshold is reached, or is expected to be reached Federal Register 69 FR 17329, 

April 2, 2004. There is an annual limit of 2,120 shallow sets north of the equator. Vessel operators must obtain single 

shallow set certificates from NMFS, which are transferable, and valid for one calendar year. Hawaii-based longline vessels 

are prohibited from making more shallow-sets north of the equator during a trip than the number of valid shallow-set 

certificates on board the vessel. Within 72 hours of landing a pelagic management unit species, vessel operators are 

required to submit one valid shallow-set certificate to the Regional Adminstrator for every shallow set fished north of the 

equator during a fishing trip. On 14 March 2006, the Western Pacific Regional Fishery Management Council voted to 

initiate an emergency closure of the Hawaii longline swordfish fishery because the fishery had already reached allowable 

interaction levels with loggerhead turtles in 2006. The shallow set component of the fishery north of the equator was 

closed on 20 March 2006 (Federal Register 71 FR 14824, 24 March 2006). 

Management type: Federal limited access program. This fishery is managed under a Fishery Management Plan (FMP), 

developed by the Western Pacific Fishery Management Council and NMFS. 

Comments: This Hawaii longline fishery is active year-round and targets swordfish and tuna, other species are caught 

incidentally. Interactions with bottlenose dolphins, false killer whales, humpback whales, short-finned pilot whales, 

spinner dolphins, short-beaked common dolphins, pantropical spotted dolphins, Blainville’s beaked whale, sperm whales, 

and Risso’s dolphins have been documented2

. Longline hooks have also been recovered from Hawaiian monk seals, but 

these were not observed during longline fishing operations. Due to interactions with protected species, especially turtles,

this fishery has been observed since February 24, 1994. Initially, observer coverage was less than 5%, increased to 10% in 

2000, and has exceeded 20% in 2001 and 2002. In 2003, observer coverage was 22.2% (based on vessel departures), with 

6.4 million hooks observed from 3,204 sets. Observed injuries of marine mammals in this fishery in 2003 included 2 false 

killer whales, 1 unidentified cetacean and 1 unidentified whale. Additionally, there was one observed mortality of a 

bottlenose dolphin (Pacific Islands Regional Office preliminary report dated 9 February 2004). In 2004, observer coverage 

was 24.6% (based on vessel departures), with 7.9 million hooks observed from 3,958 sets. Observed injuries of marine 

 

2

 K.A. Forney 2004. Estimates of cetacean mortality and injury in two U.S. Pacific longline fisheries, 1994-2002. 

Southwest Fisheries Science Center Administrative Report LJ-04-07, available from Southwest Fisheries Science Center, 

8604 La Jolla Shores Drive, La Jolla, CA 92037. 17 pp. 

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mammals in this fishery in 2004 included 5 false killer whales, 1 humpback whale and 1 short-finned pilot whale. 

Additionally, there was one observed mortality of a false killer whale. In the shallow set component of this fishery, 

observer coverage in 2004 was 100% (88 sets and 76,750 hooks observed). No marine mammal interactions were observed 

in the shallow set component of the fishery (Pacific Islands Regional Office preliminary report dated 25 January 2005). 

Category II, CA yellowtail, barracuda, white seabass, and tuna drift gillnet fishery (>3.5 and <14 in mesh) 

Note: This fishery has developed recently as an offshoot of the “CA other species, large mesh (>3.5 in) set gillnet 

fishery” (see above). Fishermen use the same gear as in the set gillnet fishery (typically 6.5 inch mesh nets, 100-200 

fathoms in length, except that they instead utilize drifting nets to target white seabass and yellowtail. Albacore tuna and 

barracuda are also targeted in this fishery. 

Number of permit holders: There are approximately 24 active permit holders in this fishery. 

Total effort: From 1999-2003, there were 140, 173, 111, 195, and 202 small-mesh drift gillnet sets fished, respectively, as 

determined from California Department of Fish and Game logbook data. 

Geographic range: This drift gillnet component of this fishery operates primarily south of Point Conception. Observed sets 

have been clustered around Santa Cruz Island, the east Santa Barbara Channel, and Cortez and Tanner Banks. Some effort 

has also been observed around San Clemente Island and San Nicolas Island. 

Seasons: This fishery operates year round. Targeted species is typically determined by market demand on a short-term 

basis. 

Gear type and fishing method: Typical gear used for this fishery is a 150-200 fathom gillnet, which is allowed to drift. The 

mesh size depends on the target species but typical values observed are 6.0 and 6.5 inches. 

Regulations: This fishery is managed by the California Dept. of Fish and Game in accordance with state and federal laws. 

Management type: This fishery is a limited entry fishery with gear restrictions and area closures. 

Comments: This fishery primarily targets white seabass and yellowtail, but also targets barracuda and albacore tuna. 

From 2002-2004, there have been 66 sets observed from 17 vessel trips. Marine mammal mortalities have included two 

long-beaked common dolphin and 3 California sea lions. Also, 4 California sea lions were entangled and released alive 

during this period. In 2003, there was one coastal bottlenose dolphin stranded with 3.5-inch gillnet wrapped around its 

tailstock, the responsible fishery is unknown. 

Category II, CA swordfish longline fishery 

Number of permit holders: As recently as 2004, there were 20-30 vessels participating in the fishery. Only one vessel was 

active in 2005. This decline in participation was due to the prohibition in shallow set swordfishing east of W150 longitude. 

Number of active permit holders: In January 2006, there was only one vessel participating in this fishery, which fished for 

tuna using deep set methods outside the U.S. EEZ. The remaining vessels from this fishery now participate in the Hawaii 

longline fishery. 

Total Effort: An estimated 1 - 1.5 million hooks were fished annually when 20-30 California-based vessels participated in 

the fishery. In 2005, there were only two trips fished by one vessel. Ten sets were observed in the first trip and it is 

unknown how many sets were made during the second trip because no observer was present. 

Geographic range: The fishery management plan (FMP) for highly migratory species prohibits targeting swordfish with 

shallow set fishing methods east of W150 longitude. In March 2006, the Pacific Fishery Management Council approved an 

application for an exempted fishing permit (EFP) that would allow one vessel to utilize shallow set longline methods within 

the U.S. EEZ, with the same shallow-set regulations used in the Hawaii fishery (circle hooks and fish bait). An 

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environmental assessment of this proposal will be prepared by the Highly Migratory Species Management Team (HMSMT) 

for review at a future Council meeting. This EFP would be effective no sooner than 2007 if it receives final approval. 

Seasons: The fishery operates year-round. 

Gear type: Typically, vessels fish 24-72 km of mainline, rigged with 22 m gangions at approximately 60 m intervals. 

Anywhere from 800 to 1,300 hooks are deployed in a set, with large squid (Illex sp.) used for bait. Variously colored 

lightsticks are used, for fishing takes place primarily during the night, when more swordfish are available in surface waters. 

The mainline is deployed in 4-7 hours and left to drift unattached for 7-10 hours. Retrieval typically takes about 7-10 

hours. A description of the gear used for deep sets targeting tuna is given in the Hawaii longline fishery section. 

Regulations: Longline vessels are prohibited from operating within the 200 nmi limit, but may unload their catch in 

California ports and are required to have a California state commercial fishing license. 

Management type: The California longline fishery is managed under a Highly Migratory Species Fishery Management 

Plan (FMP) developed by the Pacific Fishery Management Council and NMFS. The FMP was partially approved by 

NMFS on February 4, 2004. NMFS published a final rule on March 11, 2004 which prohibits shallow longline sets of the 

type normally targeting swordfish on the high seas in the Pacific Ocean east of 150 ̊ W. longitude. A mandatory observer 

program became effective for this fishery in August 2002. 

Comments: Between October 2001 and February 2004, 23 trips were observed by California-based longline observers, 

with 469 sets observed (<15% observer coverage). Between October 2001 and November 2003 the longline observer 

program reported one injured Risso’s dolphin and one unidentified dolphin killed. Examination of photographs of the dead 

dolphin led marine mammal identification experts to conclude that the animal was most likely a striped dolphin. 

Category II, California Anchovy, Mackerel, and Tuna Purse Seine Fishery. 3

Number of permit holders: There are 63 limited entry permits (Pacific Fishery Management Council. 2005. Status of the 

Pacific Coast coastal pelagic species fishery and recommended acceptable biological catches. Stock assessment and fishery 

evaluation – 2005). 

Number of active permit holders: There are 61 vessels actively fishing. 

Total effort: The fishery is managed under a capacity goal, with gross tonnage of vessels used as a proxy for fishing 

capacity. Capacity for the fleet is approximately 5,400 gross tons. Harvest guidelines for sardine and mackerel are also set 

annually. 

Geographic range: These fisheries occur along the coast of California predominantly from San Pedro, including the 

Channel Islands, north to San Francisco. 

Seasons: This fishery operates year round. Targeted species vary seasonally with availability and market demand. 

Gear type and fishing method: Purse seine, drum seine and lampara nets utilizing standard seining techniques. 

Regulations: This is a limited entry fishery. 

Management type: The fishery is managed under a Coastal Pelagic Species Fisheries Management Plan developed by the 

Pacific Fishery Management Council and NMFS. 

 

 

3 Information for this fishery came from the following sources: Pacific Fishery Management Council. 2005. Status of the Pacific Coast coastal pelagic 

species fishery and recommended acceptable biological catches. Stock assessment and fishery evaluation – 2005; California Coastal Pelagic Species Pilot 

Observer Program Informational Report 12 October 2005 (NMFS SW Region, unpublished); Lyle Enriquez NMFS Southwest Regional Office (personal 

communication) and the Marine Mammal Authorization Program, Registration and Reporting System.

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A NMFS pilot observer program began in July 2004 and has continued through January 2006. A total of 33 sets have been 

observed with one California sea lion observed killed, five sea lions released alive, and one sea otter released alive. Under 

the MMAP self-reporting program, the following mortalities have been reported: In 2003, four California sea lions 

drowned after chewing through a bait barge net used by the anchovy lampara net fishery. 

 

Category II, California Sardine Purse Seine Fishery3

. 

Note: This fishery was previously listed as part of the ‘CA round haul fisheries’ in Appendix 1 of the 2005 U.S. Pacific 

Marine Mammal Stock Assessment Reports. The CA round haul fishery category has been divided into the CA anchovy, 

mackerel, and tuna purse (see above) and CA sardine purse seine fishery, respectively. 

Number of permit holders: There are 63 limited entry permits (Pacific Fishery Management Council. 2005. Status of the 

Pacific Coast coastal pelagic species fishery and recommended acceptable biological catches. Stock assessment and fishery 

evaluation – 2005). 

Number of active permit holders: There are 61 vessels actively fishing. 

Total effort: The fishery is managed under a capacity goal, with gross tonnage of vessels used as a proxy for fishing 

capacity. Capacity for the fleet is approximately 5,400 gross tons. 

Geographic range: These fisheries occur along the coasts of California, Oregon, and Washington. 

 

Seasons: This fishery operates year round. Targeted species vary seasonally with availability and market demand. 

Gear type and fishing method: Purse seine, drum seine and lampara nets utilizing standard seining techniques. 

Regulations: This is a limited entry fishery. 

Management type: The fishery is managed under a Coastal Pelagic Species Fisheries Management Plan developed by the 

Pacific Fishery Management Council and NMFS. 

Comments: A NMFS pilot observer program began in July 2004 and has continued through January 2006. A total of 74 

sets have been observed, with 49 California sea lions and one four harbor seals released alive. The following marine 

mammal mortalities have been reported in this fishery under the MMAP self-reporting program. In 2004, one sea lion 

drowned during fishing operations in the sardine drum seine fishery. 

Category II, WA Puget Sound Region salmon drift gillnet fishery.

Number of permit holders: This commercial fishery includes all inland waters south of the US-Canada border and east of 

the Bonilla/Tatoosh line, at the entrance to the Strait of Juan de Fuca. Treaty Indian salmon gillnet fishing is not included 

in this commercial fishery. In 1999, the U.S. and Canada reached an agreement that significantly reduced the U.S. share of 

sockeye salmon. In order to compensate the non-treaty U.S. fishermen for the impact of this reduction, a federally funded 

buyback program was established. By the 2001 fishing season, the number of available drift gillnet permits had been 

reduced from 675 (1999) to 216. The intent of the buyback program was to reduce the number of drift gillnet permits to 

200 (pers. comm., David Cantillon, NMFS, Northwest Region). 

Number of active permit holders: Under the cooperative program that integrates issuance of Marine Mammal 

Authorization Certificates into the existing State license process, NMFS receives data on vessels that have completed the 

licensing process and are eligible to fish. These vessels are a subset of the total permits extant (725 in 2001), and the 

remainder of the permits are inactive and do not participate in the fishery during a given year. The number of "active" 

permits is assumed to be equal to or less than the number of permits that are eligible to fish. From 1997-2001, the number 

of active permits was 633, 559, 199, 248, and 182, respectively. 

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Total effort: Effort in the Puget Sound salmon drift gillnet fishery is regulated by systematic openings and closures that are 

specific to area and target salmon species. Since 1994, the number of active vessels in the Puget Sound drift gillnet fishery

has declined. In addition, at least one major portion of the fishery, the previously observed sockeye fishery in areas 7 and 

7A, has experienced reductions in available fishing time (openings). The number of days and total number of hours that the 

sockeye fishery remained open, approached the 1994 level only once (1997) in the period from 1995 through 1998. In the 

remaining years the available sockeye fishing time was less than half of the 1994 level. In recent years, poor sockeye 

returns and market conditions have combined to reduce participation in the fishery beyond the reductions created originally 

by the federal buyback program. In 2001, drift gillnets fished for only one opening and 182 gear units were fished in all 

areas as compared to the 559 cited for 1998. Owing to the buyback program and reduced salmon runs, it is expected that 

the number of active permits will remain low. 

Geographic Range: The fishery occurs in the inland marine waters south of the U.S./Canada border and east of the 

Bonilla/Tatoosh line at the entrance to the Strait of Juan de Fuca. The inland waters are divided into smaller statistical 

catch areas which are regulated independently. 

Seasons: This fishery has multiple seasons throughout the year that vary among local areas dependent on local salmon 

runs. The seasons are managed to access harvestable surplus of robust stocks of salmon while minimizing impacts on weak 

stocks. 

Gear type and fishing methods: Vessels operating in this fishery use a drift gillnet of single web construction, not 

exceeding 300 fathoms in length. Minimum mesh size for gillnet gear varies by target species. Fishing directed at sockeye 

and pink salmon are limited to gillnet gear with a 5 inch minimum mesh and a 6 inch maximum, with an additional "bird 

mesh" requirement that the first 20 meshes below the corkline be constructed of 5 inch opaque white mesh for visibility; the 

chinook season has a 7 inch minimum mesh; the coho season has a 5 inch minimum mesh; and the chum season has a 6 to 

6.25 inch minimum mesh. The depth of gillnets can vary depending upon the fishery and the area fished. Normally they 

range from 180 to 220 meshes in depth, with 180 meshes as a common depth. It is the intention of the fisher to keep the net 

off the bottom. The vessel is attached to one end of the net and drifts with the net. The entire net is periodically retrieved 

onto the vessel and catch is removed. Drift times vary depending on fishing area, tidal condition and catch. 

Regulations: The fishery is a limited entry fishery with seasonal openings, area closures, and gear restrictions. 

Management type: The fishery occurs in State waters and is managed by the Washington Department of Fish and Wildlife 

consistent with the U.S.-Canada Pacific Salmon Commission management regimes and the ocean salmon management 

objectives of the Pacific Fishery Management Council. U.S. and Canadian Fraser River sockeye and pink salmon fisheries 

are managed by the bilateral Fraser Panel in Panel Area waters. This includes the entire U.S. drift gillnet fishery for Fraser

sockeye and pink salmon. For U.S. fisheries, Fraser Panel Orders are given effect by federal regulations that consist of Inseason Orders issued by the NMFS Regional Administrator of the NMFS Northwest Region. These regulations are filed in 

the Federal Register post-season. 

Comments: In 1993, observers were placed onboard vessels in a pilot program to monitor seabird and marine mammal 

interactions with fishing effort for several target salmon species in a number of areas throughout the Puget Sound region. 

In 1994 observer effort was concentrated in the sockeye fishery in areas 7 and 7A, where interactions with seabirds and 

marine mammals were most likely to occur. Incidental takes of harbor porpoise, Dall’s porpoise and harbor seals have been 

documented in the fishery. The overall take of marine mammals for the salmon drift gillnet fisheries in Puget Sound is 

unlikely to have increased since the fisheries were last observed, owing to reductions in the number of participating vessels 

and available fishing time. 

Category II, OR swordfish surface longline fishery.

Number of permit holders: The number of permits issued annually from 2000-2005 has ranged between one and seven 

(pers. comm., Jean McCrae, Oregon Department of Fish and Wildlife, Marine Resources Program). 

Number of active permit holders: Based on landings of swordfish with this gear type, there were no active permit holders 

in this fishery from 2000-2005. 

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Total effort: From 2000-2005, there were no reported swordfish landings using longline gear. 

Geographic range: The Fishery Management Plan prohibits targeting highly migratory species such as swordfish with 

longlines within the U.S. EEZ, thus any fishing would have to occur outside the EEZ. However, shallow set methods used 

for swordfish are also prohibited east of W150 longitude. 

Seasons: This fishery could occur year-round, however, effort would generally terminate by late fall. 

Gear type: Fishing gear consists of a buoyed mainline fitted with leaders and baited hooks. The mainline is fished near the 

surface suspended from buoys (rather than anchored to the bottom as in groundfish longline fisheries). Swordfish longlines 

may not exceed 1000 fathoms in length and must be attached at one end to the vessel when fishing. The gear is typically 

set in the evening and retrieved in the morning. 

Regulations: The fishery is a limited entry fishery with gear and bycatch restrictions. 

Management type: The fishery is managed under a Highly Migratory Species Fisheries Management Plan developed by 

the Pacific Fishery Management Council and NMFS. 

Category II, OR blue shark surface longline fishery.

Number of permit holders: The number of Oregon Developmental Fishery Permits for fishing blue shark using a floating 

longline is limited to 10. From 2000-2005, there were fewer than 5 permits issued annually for this fishery (pers. comm., 

Jean McCrae, Oregon Department of Fish and Wildlife, Marine Resources Program). 

Number of active permit holders: There were no active permits in the blue shark longline fishery off Oregon from 2000-

2005. The effort in this fishery prior to 1998 was estimated to be low based on the number of permits issued and very 

limited landings. 

Total effort: From 2000-2005, there were no reported landings of blue shark using longline gear. 

Geographic range: This fishery occurs off the coast of Oregon. The Fishery Management Plan prohibits targeting highly 

migratory species such as blue sharks with longlines within the U.S. EEZ, thus any fishing would have to occur outside the 

EEZ. 

 

Seasons: This fishery occurs year-round, however, effort in this fishery generally terminates by late fall. 

Gear type: Fishing gear consists of a buoyed mainline fitted with leaders and baited hooks. The mainline is fished near the 

surface suspended from buoys (rather than anchored to the bottom as in groundfish longline fisheries). Shark longlines 

must be marked at each terminal surface end with a pole and flag, an operating light, a radar reflector, and a buoy showing 

clear identification and gear owner. The gear is typically set in the evening and retrieved in the morning. 

Regulations: The fishery is a limited entry fishery with gear and bycatch restrictions. 

Management type: The fishery is managed under a Highly Migratory Species Fisheries Management Plan developed by 

the Pacific Fishery Management Council and NMFS. 

Category II, CA squid purse seine fishery.4

 

4

This fishery description was provided by Dale Sweetnam, Senior Biologist at CDFG La Jolla. 

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Number of permit holders: A permit to participate in the squid fishery has been required since April 1998. There are two 

types of permits. Market squid vessel permits allow a light vessel to attract squid with lights and catch squid. Light boat 

owner permits only allow the use of attracting lights to aggregate market squid. In the 2002/2003 season there were 184 

market squid vessel permits and 40 light boat owner permits issued. Landings of two tons or less are considered incidental 

and no permit is required. 

Number of active permit holders: The number of active permits varies by year depending on market conditions and squid 

availability. During the 2002/2003 season, there were approximately 105 vessels active during some portion of the year. 

Thirty-four vessels harvested 90% of the total landings greater than two tons. The 1999/2000 season had the highest squid 

landings to date, with 132 vessels making squid landings greater than two tons. 

Total effort: Beginning in May 2000, logbooks were required for the squid fishery. Results for the 2001 calendar year 

indicate that each hour of fishing required 5.5 hours of search time by light boats. Combined searching and fishing effort 

resulted in 3.7 mt of catch per hour. In the 2002/2003 season, the fishery made 2,244 landings. This is a 34.0% decrease 

from the previous season. In addition, the average landing decreased from 28.2 mt to 19.0 mt. 

Geographic range: Since the mid-1980s, the majority of the squid fishing harvest has occurred south of Point Conception. 

However, during the 2002/2003 season, a moderate El Nino condition resulted in nearly 60% of the catch landed in 

northern California. The northern fishery harvest ranged from Morro Bay to Fort Bragg, although the majority of fishing 

occurred within a half mile of the Monterey Bay shoreline. The Monterey Bay fishery has been in operation since the mid1800s and has historical significance for California. Squid catch south of Point Conception accounted for only 41% of the 

2002/2003 landings and declined 54% from 84,024 mt in the previous season to 17,387 mt. 

Seasons: This fishery occurs year-round, however, effort in this fishery differs north and south of Point Conception. 

Typically, the fishery north of Point Conception operates from April through September while the southern fishery is most 

active from October through March. El Niño conditions hamper the fishery and squid landings are minimal during these 

events, while landings in the northern fishery often increase. The La Niña event in 1999 resulted in the southern fishery 

landing squid year-round. 

Gear type: There are several gears employed in this fishery. From 1997-2001, the vast majority (98%) of vessels uses 

either purse (77%) or drum (21%) seine nets. Other types of nets used include lampara, dip and brail nets which are used 

by a few vessels in southern California. Another gear type associated with the market squid fishery is attracting lights that 

are used to aggregate spawning squid. In 2000, attracting lights were regulated and each vessel is now restricted to no more 

than 30,000 watts of lights during fishing activities. Further, to reduce light scatter, lights must be shielded and oriented 

directly downward. The lighting restrictions were enacted to avoid risks to nesting brown pelicans and interactions with 

other seabird species of concern. 

Regulations: All vessels participating in the squid fishery must have a permit. Commercial squid fishing is prohibited 

between noon on Friday and noon on Sunday of each week to allow a two-day consecutive uninterrupted period of 

spawning. A mandatory logbook program for fishing and lighting vessels has been in place since May 2000. In May 2001, 

a seasonal harvest guideline of 125,000 short tons for market squid was established to limit further expansion of the fishery. 

Management type: This fishery was largely unregulated until 1998 when it came under more strict regulatory control by 

the Department of Fish and Game. The fishery is considered a monitored fishery in the Pacific Fishery Management 

Council’s Coastal Pelagic Species Fishery Management Plan. A state fishery management plan is to be adopted by the Fish 

and Game Commission by December 2004. The plan considers seasonal and daily catch limitations; weekend closures, 

research and monitoring programs, harvest replenishment areas, live bait and incidental market squid catch, restricted 

access programs including transferability, gear restrictions, area and time closures to address seabird issues, and permit 

fees. 

 

Comments: The squid fishery operates primarily at night and targets spawning aggregations with the use of lights. 

Encounters between the fishery and pilot whales, pinnipeds, dolphins, and birds have been documented. Seal bombs are 

used regularly. A pilot observer program began in July 2004 and has documented one unidentified common dolphin 

mortality in 135 sets through January 2006. In addition, there have been 96 California sea lions and three harbor seals 

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released alive (NMFS, Southwest Region, unpublished data). In addition to these observed mortalities, there were three 

strandings of Risso’s dolphin from 2002-2003 where evidence of gunshot wounds was confirmed, suggesting interaction 

with this fishery (NMFS Southwest Regional Office, unpublished data). Lethal and nonlethal interaction rates are 

unknown. During the 1980s, California’s squid fishery grew rapidly in fleet size and landings when international demand 

for squid increased due to declining squid fisheries in other parts of the world. In 1997, the rapid growth of fleet size was 

halted by a moratorium on new permits. Landing records were set several times during the 1990s, but have been curtailed 

with the establishment of the 125,000 short ton seasonal harvest guideline. 

Category III, CA herring gillnet fishery.5

 The herring fishery is concentrated in four spawning areas which are managed separately by the California Department of 

Fish and Game (CDFG); catch quotas are based on population estimates derived from acoustic and spawning-ground 

surveys. The largest spawning aggregations occur in San Francisco Bay and produces more than 90% of the herring catch. 

Smaller spawning aggregations are fished in Tomales Bay, Humboldt Bay, and Crescent City Harbor. During the early 

1990's, there were 26 round haul permits (either purse seine or lampara nets). Between 1993 and 1998, all purse seine 

fishers converted their gear to gillnets with stretched mesh size less than 2.5 inches (which are not known to take mammals) 

as part of CDFG efforts to protect herring resources. The fishery is managed through a limited-entry program. The 

California Department of Fish and Game website lists a total of 447 herring gillnet permits for 2005 

(http://www.dfg.ca.gov/mrd/herring/index.html). Of these, 406 permits exist for San Francisco Bay, 34 in Tomales Bay, 4 

in Humboldt Bay, and 3 in Crescent City Harbor. This fishery begins in December (San Francisco Bay) or January 

(northern California) and ends when the quotas have been reached, but no later than mid-March. 

 

Category III, WA Willapa Bay salmon drift gillnet fishery. 

Number of permit holders: The total number of permit holders for this fishery in 1995 and 1996 was 300 but this number 

has declined in subsequent years. In 1997 there were 264 total permits and 243 in 1998. The NMFS 2001 List of Fisheries 

lists an estimate of 82 vessels/persons in this fishery. 

Number of active permit holders: The number of active permit holders is assumed to be equal to or less than the number of 

permits eligible to fish in a given year. The number of permits renewed and eligible to fish in 1996 was 300 but declined to 

224 in 1997 and 196 permits were renewed for 1998. The 1996-98 counts do not include permits held on waivers for those 

years, but do include permits that were eligible to fish at some point during the year and subsequently entered into a 

buyback program. The number of permits issued for this fishery has been reduced through a combination of State and 

federal permit buyback programs. Vessels permitted to fish in the Willapa Bay are also permitted to fish in the lower 

Columbia River drift gillnet fishery. 

 

Total effort: Effort in this fishery is regulated through area and species openings. The fishery was observed in 1992 and 

1993 when fishery opening were greater than in recent years. In 1992 and 1993 there were 42 and 19 days of open fishing 

time during the summer "dip-in" fishery. The "dip-in" fishery was closed in 1994 through 1999. Available openings have 

also declined in the fall chinook/coho fisheries. In 1992/93 respectively there were 44 and 78 days of available fishing 

time. There were 43, 45, 22 and 16.5 available open fishing days during 1995 through 1998. 

Geographic range: This fishery includes all inland marine waters of Willapa Bay. The waters of the Bay are further 

divided into smaller statistical catch areas. 

Seasons: Seasonal openings coincide with local salmon run timing and fish abundance. 

Gear type: Fishing gear used in this fishery is a drift gillnet of single web construction, not exceeding 250 fathoms in 

length, with a minimum stretched mesh size ranging upward from 5 inches depending on target salmon species. The gear is 

commonly set during periods of low and high slack tides. It is the intention of the fisher to keep the net off the bottom. 

The vessel is attached to one end of the net and drifts with the net. The entire net is periodically retrieved onto the vessel

and catch is removed. Drift times vary depending on fishing area, tidal condition, and catch. 

 

5

 Pers. Comm. Becky Ota, State Herring Manager, Senior Biologist. 

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Regulations: This fishery is a limited entry fishery with seasonal openings and gear restrictions. 

Management type: The salmon drift gillnet fishery is managed by the Washington Department of Fish and Wildlife. 

Comments: Observers were placed onboard vessels in this fishery to monitor marine mammal interactions in the early 

1980s and in 1990-93. Five incidentally taken harbor seals were recovered by observers in the fishery from 1991through 

1993 (3 in ‘92 and 2 in ‘93). Two incidentally taken northern elephant seals were recovered by observers from the fishery 

in 1991 but no takes of this species were observed. The summer fishery (July- August) in Willapa Bay has been closed 

since it was last observed in 1993 and available fishing time declined from 1996 through 1998. 

Category III, WA Grays Harbor salmon drift gillnet fishery. 

Number of permit holders: This commercial drift gillnet fishery does not include Treaty Indian salmon gillnet fishing. 

The total number of permit holders for this commercial fishery in 1995 and 1996 was 117 but this number has declined in 

subsequent years. In 1997 there were 101 total permits and 87 in 1998. 

Number of active permit holders: The NMFS 2001 List of Fisheries lists a total of 24 vessels/persons operating in this 

fishery. The number of active permit holders is assumed to be equal to or less than the number of permits eligible to fish in 

a given year. The number of permits renewed and eligible to fish in 1996 was 117 but declined to 79 in 1997 and 59 

permits were renewed for 1998. The 1996-98 counts do not include permits held on waivers for those years but do include 

permits that were eligible to fish at some point during the year and subsequently entered a buyback program. The number 

of permits issued for this fishery has been reduced through a combination of State and federal permit buyback programs. 

Vessels permitted to fish in Grays Harbor are also permitted to fish in the lower Columbia River salmon drift gillnet 

fishery. 

Total effort: Effort in this fishery is regulated through area and species openings. The fishery was observed in 1992 and 

1993 when fishery openings were greater than in recent years. In 1992 and 1993 there were 42 and 19 days of open fishing 

time during the summer "dip-in" fishery. The "dip-in" fishery was closed in 1994 through 1999. Available openings have 

also declined in the fall chinook/coho fisheries. There were 11, 17.5, 9 and 5 available open fishing days during the 1995 

through 1998 fall season. 

Geographic range: Effort in this fishery includes all marine waters of Grays Harbor. The waters are further divided into 

smaller statistical catch areas. 

Seasons: This fishery is subject to seasonal openings which coincide with local salmon run timing and fish abundance. 

Gear type: Fishing gear used in this fishery is a drift gillnet of single web construction, not exceeding 250 fathoms in 

length, with a minimum stretched mesh size ranging of 5 inches depending on target salmon species. The gear is 

commonly set during periods of low and high slack tides and retrieved periodically by the tending vessel. It is the intention 

of the fisher to keep the net off the bottom. The vessel is attached to one end of the net and drifts with the net. The entire 

net is periodically retrieved onto the vessel and catch is removed. Drift times vary depending on fishing area, tidal 

condition, and catch. 

Regulations: The fishery is a limited entry fishery with seasonal openings and gear restrictions. 

Management type: The salmon drift gillnet fishery is managed by the Washington Department of Fish and Wildlife. 

Comments: Observers were placed onboard vessels in this fishery to monitor marine mammal interactions in the early 

1980s and in 1990-93. Incidental take of harbor seals was observed during the fishery in 1992 and 1993. In 1992, one 

harbor seal was observed entangled dead during the summer fishery and one additional seal was observed entangled during 

the fall fishery but it escaped uninjured. In 1993, one harbor seal was observed entangled dead and one additional seal was 

recovered by observers during the summer fishery. The summer fishery (July-August) in Grays Harbor has been closed 

since it was last observed in 1993. Available fishing time in the fall chinook fisheries declined from 1996 through 1998. 

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Category III, WA, OR lower Columbia River salmon drift gillnet fishery.

Number of permit holders: The total number of permit holders was 856 (344 from Oregon and 512 from Washington) 

when the fishery was last observed in 1993. In 1995 through 1998 the number of permits was 747, 693, 675 and 620 

respectively. The number of permits issued for this fishery by Washington has been reduced through a combination of 

State and federal buy-back programs. This reduction is reflected in the overall decline in the total number of permits. 

 

Number of active permit holders: The number of active permits is a subset of the total permits issued for the fishery. For 

example, in 1995, 110 vessels (of the 747 vessels holding permits) landed fish in the mainstem fishery. 

Total effort: Effort in this fishery is regulated through species related seasonal openings and gear restrictions. The fishery 

was observed in 1991, 1992 and 1993 during several seasons of the year. The winter seasons (openings) for 1991 through 

1993 totaled 13, 9.5, and 6 days respectively. The winter season has subsequently been reduced to remnant levels to protect 

upriver ESA listed salmon stocks. In 1995 there was no winter salmon season, in 1996 the fishery was open for 1 day. In 

1997 and 1998 the season was shifted to earlier in the year and gear restrictions were imposed to target primarily sturgeon. 

The fall fishery in the mainstem was also observed 1992 and 1993 as was the Young's Bay terminal fishery in 1993, 

however, no marine mammal mortalities were observed during these fisheries. The fall mainstem fishery openings varied 

from 1 day in 1995 to just under 19.5 days in 1997 and 6 days in 1998. The fall Youngs Bay terminal fishery fluctuated 

between 60 and 70 days for the 1995 through 1998 period which was similar to the fishery during the period observed. 

Geographic range: This fishery occurs in the main stem of the Columbia river from the mouth at the Pacific Ocean 

upstream to river mile 140 near the Bonneville Dam. The lower Columbia is further subdivided into smaller statistical 

catch areas which can be regulated independently. 

Seasons: This fishery is subject to season and statistical area openings which are designed to coincide with run timing of 

harvestable salmon runs while protecting weak salmon stocks and those listed under the Endangered Species Act. In recent 

years, early spring (winter) fisheries have been sharply curtailed for the protection of listed salmon species. In 1994, for 

example, the spring fishery was open for only three days with approximately 1900 fish landed. In 1995 the spring fishery 

was closed and in 1996 the fishery was open for one day but fishing effort was minimal owing to severe flooding. Only 

100 fish were landed during the one day in 1996. 

Gear type: Typical gear used in this fishery is a gillnet of single web construction, not exceeding 250 fathoms in length, 

with a minimum stretched mesh size ranging upwards from 5 inches depending on target salmon species. The gear is 

commonly set during periods of low and high slack tides. It is the intention of the fisher to keep the net off the bottom. 

The vessel is attached to one end of the net and drifts with the net. The entire net is periodically retrieved onto the vessel

and catch is removed. Drift times vary depending on fishing area, tidal condition, and catch. 

Regulations: The fishery is a limited entry fishery with seasonal openings, area closures, and gear restrictions. 

Management type: The lower Columbia River salmon drift gillnet fishery is managed jointly by the Washington 

Department of Fish and Wildlife and the Oregon Department of Fish and Wildlife. 

Comments: Observers were placed onboard vessels in this fishery to monitor marine mammal interactions in the early 

1980s and in 1990-93. Incidental takes of harbor seal and California sea lion were documented, but only during the winter 

seasons (which have been reduced dramatically in recent years to protect ESA listed salmon). No mortalities were 

observed during the fall fisheries. 

Category III, WA, OR salmon net pens.

Number of permit holders: There were 12 commercial salmon net pen (“grow out”) facilities licensed in Washington in 

1998. There are no commercial salmon net pen or aquaculture facilities currently licensed in Oregon. Non-commercial 

salmon enhancement pens are not included in the list of commercial fisheries. 

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Number of active permit holders: Twelve salmon net pen facilities in Washington. 

Total effort: The 12 licensed facilities on Washington operate year-round. 

Geographic range: In Washington, net pens are found in protected waters in the Straits (Port Angeles), northern Puget 

Sound (in the San Juan Island area) as well as in Puget Sound south of Admirality Inlet. There are currently no commercial 

salmon pens in Oregon. 

Seasons: Salmon net pens operate year-round. 

Gear type: Net pens are large net impoundments suspended below a floating dock-like structure. The floating docks are 

anchored to the bottom and may also support guard (predator) net systems. Multiple pens are commonly rafted together 

and the entire facility is positioned in an area with adequate tidal flow to maintain water quality. 

Regulations: Specific regulations unknown. 

Management type: In Washington, the salmon net pen fishery is managed by the Washington Department of Natural 

Resources through Aquatic Lands Permits as well as the Washington Department of Fish and Wildlife. 

Comments: Salmon net pen operations have not been monitored by NMFS for marine mammal interactions, however, 

incidental takes of California sea lions and harbor seals have been reported. 

Category III, WA, OR, CA groundfish trawl. 

Approximate number of vessels/persons: In 1998, approximately 332 vessels used bottom and mid-water trawl gear to 

harvest Pacific coast groundfish. This is down from 383 vessels in 1995. The NMFS List of Fisheries for 2001 lists 585 

vessels as participating in this fishery. Groundfish trawl vessels harvest a variety of species including Pacific hake, flatfish, 

sablefish, lingcod, and rockfish. This commercial fishery does not include Treaty Indian fishing for groundfish. 

All observed incidental marine mammal takes have occurred in the mid-water trawl fishery for Pacific hake. The annual 

hake allocation is divided between vessels that harvest and process catch at sea and those that harvest and deliver catch to 

shore-based processing facilities. At least one NMFS-trained observer is placed on board each at-sea processing vessel to 

provide comprehensive data on total catch, including marine mammal takes. In the California, Oregon, and Washington 

range of the fishery, the number of vessels fishing ranged between 12 and 16 (all with observers) during 1997-2001. Hake 

vessels that deliver to shore-based processors are issued Exempted Fishing Permits that requires the entire catch to be 

delivered unsorted to processing facilities where State technicians have the opportunity to sample. In 1998, 13% of the 

hake deliveries landed at shore-based processors were monitored. The following is a description of the commercial hake 

fishery. 

Number of permit holders/active permit holders: A license limitation ("limited entry") program has been in effect in the 

Pacific coast groundfish fishery since 1994. The number of limited entry permits is limited to 404. Non-tribal trawl vessels 

that harvest groundfish are required to possess a limited entry permit to operate in the fishery. Any vessel with a federal 

limited entry trawl permit may fish for hake, but the number of vessels that do is smaller than the number of permits. In 

1998, approximately 61 limited entry vessels, 7 catcher/processors and 50 catcher vessels delivering to shoreside and 

mothership processors, made commercial landings of hake during the regular season. In addition, 6 unpermitted 

mothership processors received unsorted hake catch. 

 

Total effort: The hake allocation continues to be fully utilized. From 1997 to 1999 the annual allocation was 232,000 

mt/year, this is an increase over the 1996 allocation of 212,000 mt and the 1995 allocation of 178,400 mt. In 1998, 

motherships vessels received 50,087 mt of hake in 17 days, catcher/processors took 70,365 mt of hake in 54 days and 

shore-based processors received 87,862 mt of hake over a 196 day period. 

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Geographic range: The fishery extends from northern California (about 40o 30' N. latitude) to the U.S.-Canada border. 

Pacific hake migrate from south to north during the fishing season, so effort in the south usually occurs earlier than in the 

north. 

Seasons: From 1997 to 1999, season start dates have remained unchanged. The shore-based season in most of the Eureka 

area (between 42O- 40O30' N latitude) began on April 1, the fishery south of 40O30' N latitude opened April 15, and the 

fishery north of 42O N latitude started on June 15. In 1998, the primary season for the shore-based fleet closed on October 

13, 1998. The primary seasons for the mothership and catcher/processor sectors began May 15, north of 420

 N. lat. In 

1998, the mothership fishery closed on May 31, the catcher/processor fishery closed on August 7. 

Gear type: The Pacific hake trawl fishery is conducted with mid-water trawl gear with a minimum mesh size of 3 inches 

throughout the net. 

Regulations/Management type: This fishery is managed through federal regulations by the Pacific Fishery Management 

Council under the Groundfish Fishery Management Plan. 

Comments: Since 1991, incidental takes of Steller sea lions, Pacific white-sided dolphin, Dall's porpoise, California sea 

lion, harbor seal, northern fur seal, and northern elephant seal have been documented in the hake fishery. From 1997-2001, 

4 California sea lions, 2 harbor seals, 2 northern elephant seals, 1 Pacific white-sided dolphin, and 6 Dall’s porpoise were 

reported taken in California/Oregon/Washington regions by this fishery. 

 

Category III, Hawaii gillnet fishery.6

Number of active permit holders: In 1997 there were 129 active commercial fishers. In 1995 there were approximately 

115. 

Total effort: In 1997 there were 2,109 trips for a total catch of 864,194 pounds with 792,210 pounds sold. This fishery 

operates in nearshore and coastal pelagic regions. 

Seasons: This fishery operates year-round with the exception of Juvenile big-eyed scad less than 8.5 inches which cannot 

be taken from July through October. 

Gear type: Gillnets of stretched mesh greater than 2 inches and stretched mesh size greater than 2.75 inches for stationary 

gillnets. Stationary nets must be inspected every 2 hours and total soak time cannot exceed four hours in the same location. 

New restrictions implemented in 2002 include that nets may not: 1) be used more than once in a 24-hour period; 2) exceed 

a 12 ft stretched height limit; 3) exceed a single-panel; 4) be used at night; 5) be set within 100 ft. of another lay net; 6) be 

set in more than 80 ft depths; 7) be left unattended for more than 1⁄2 hour; 8) break coral during retrieval and nets must be 1) 

registered with the Division of Aquatic Resources; 2) inspected within two hours after being set; 2) tagged with two marker 

buoys while fished. In addition to these gear restrictions, non-commercial users of lay nets may not use a net longer than 

500 ft, while commercial users may use nets up to 1200 ft in length. Additional mesh restrictions are in place for taking the 

big-eyed scad. 

Regulations: Gear and season restrictions (see above). 

Management type: Managed by the State of Hawaii Division of Aquatic Resources. 

Comments: The principle catches include reef fishes and big-eyed scad (akule) and mackerel scad (opelu). Interactions 

have been documented with bottlenose dolphin and spinner dolphin. 

 

Category III, Hawaii lobster trap fishery.

7 8

 

6

Descriptions of Hawaii State managed fisheries provided by William Devick, State of Hawaii, Department of Land and 

Natural Resources, Division of Aquatic Resources, Honolulu Hawaii.

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Note: The portion of this fishery managed by the State of Hawaii and operating in the MHI is about 1% of the size (total 

pounds of lobster caught) of the federally managed fishery operating primarily in the NWHI. The description that follows 

refers to the NWHI fishery unless stated otherwise. 

Number of permit holders: There are 15 permit holders under a (1991) federal limited access program. 

Number of active permit holders: In 1998 and 1999 there were 5 and 6 vessels that participated respectively. In the MHI 

there were 5 active fishers in 1997. 

Total effort: The number of trap hauls for 1999 is not available at this time. However, the majority of the effort took place 

in the 4 harvest guideline areas; Necker Bank, Gardner Pinnacles and Maro Reef, with the remaining effort spread out over 

10 unique areas. In 1998 171,000 trap hauls were made by the 5 vessels during 9 trips and in 1997 a total of 177,700 hauls 

were made. In the MHI 19 trips were made in 1997. 

Geographic range: Lobster permits allow fishing operations in the US EEZ from 3 to 200 nmi offshore American Samoa, 

Guam and Hawaii (including the EEZ areas of the NWHI and MHI). However, no vessels have operated in the EEZ’s of 

American Samoa or Guam since 1983. 

Seasons: This fishery operates under a seasonal harvest guideline system opening on July 1. The season ends once the 

harvest guideline is met, but no later than December 31. In 1998, the harvest guideline was divided into the 4 areas 

mentioned above with total lobster catch set at (in thousands) 70, 20, 80, and 116, respectively. Area closure occurs once 

an area’s harvest guideline is met. In the MHI, open season is from September through April. 

Gear type: One string consists of approximately 100 Fathom-plus plastic lobster traps. About 10 such strings are pulled and 

set each day. Since 1987 escape vents that allow small lobsters to escape from the trap have been mandatory. In 1996, the 

fishery became “retain all”, i.e. there are no size limits or prohibitions on the retention of berried female lobsters. The 

entry-way of the lobster trap must be less than 6.5 inches to prevent monk seals from getting their heads stuck in the trap. 

In the MHI, rigid trap materials must have a dimension greater than 1 inch by 2 inches, with the trap not exceeding 10 feet 

by six feet. 

Regulations: Season, gear and quota restrictions (see above) for the NWHI were formulated by the Western Pacific 

Regional Fishery Management Council and implemented by NMFS. The MHI fishery is managed by the State of Hawaii, 

Division of Aquatic Resources with season and gear restrictions (see above). 

Management type: Limited access program with bank specific quotas and closures. In the MHI, open access. 

Comments: The NWHI fishery targets the red spiny lobster and the common slipper lobster. The ridgeback slipper lobster 

is also taken. Protected species of concern include monk seals (mentioned above) and turtles. There have been no 

interactions with these species since 1995 but they have been seen in the vicinity of the fishing gear. 

Category III, Hawaii inshore handline fishery. 

 

In 1997 a total 750 fishers made 8,526 fishing trips in the main Hawaiian Islands and caught 531,449 pounds and sold 

475,562 pounds for an ex-vessel landing value of $1,010,758. This fishery occurs in nearshore and coastal pelagic regions. 

The principal catches include reef fishes and big-eyed scad (akule) and mackerel scad (opelu). In 1995 approximately 650 

fishers were active. Interactions have been documented for bottlenose dolphin. 

 

Category III, Hawaii deep sea bottomfish handline and jig fishery. 

 7

Kawamoto, K. and Samuel G. Pooley. 1999. Draft Annual report of the 1998 western pacific lobster fishery.

8

Kawamoto, K. 1999. Summary of the 1999 NWHI Lobster Fishing Season. NMFS Honolulu Laboratory.

301
Revised 05/15/2006 Appendix 1. Description of U.S. Commercial Fisheries 

Note: There are two commercial bottomfish fisheries in Hawaii: a distant water Northwestern Hawaiian Islands (NWHI) 

limited entry fishery under federal jurisdiction and the main Hawaiian Islands bottomfish fishery primarily under the State 

of Hawaii jurisdiction. 

 

Number of permit holders: The main Hawaiian Islands fishery is open access with close to 2,000 bottomfish vessels 

registered with the State of Hawaii, whereas the NWHI is restricted to a maximum of 17 vessels. 

Number of active permit holders: In 1997 in the MHI a total of 750 fishers were active. The NWHI are divided into the 

Mau Zone (closer to MHI) and the Hoomalu Zone. The Hoomalu Zone is a limited entry zone with 6 vessels participating 

in 1998, 7 vessels fished the Mau Zone in the same year. Restrictions on new entry into the Mau Zone were implemented 

in 1998. 

Total effort: In 1998 in the MHI approximately 8,500 trips were made with a total catch of 424,000 pounds for an exvessel landing value of $1,336,000. This fishery occurs primarily in offshore banks and pinnacles. In the NWHI 332,000 

pounds ($894,000) were caught in 1998, below average since 1990. 

Seasons: Year round. 

Gear type: This fishery is a hook-and-line fishery that takes place in deep water. In the NWHI fishery, vessels are 30 ft or 

greater and conduct trips of about 10 days. In the MHI the vessels are smaller than 30 ft and trips last from 1 to 3 days. 

Regulations: In the MHI, the sale of snappers (opakapaka, onaga and uku) and jacks less than one pound is prohibited. In 

June of 1998, Hawaii Division of Aquatic Resources (HDAR) closed 19 areas to bottomfishing and regulations pertaining 

to seven species (onaga, opakapaka, ehu, kalekale, gindai, hapuupuu and lehi) were enacted. 

Management type: The MHI is managed by the HDAR with catch, gear and area restrictions (see above) but no permit 

limits. The NWHI is a limited access federal program. 

Comments: The deep-slope bottomfish fishery in Hawaii concentrates on species of eteline snappers, carangids, and a 

single species of grouper concentrated at depths of 30-150 fathoms. These fish have been fished on a subsistence basis 

since ancient times and commercially for at least 90 years. NMFS is considering the possibility of re-categorizing the 

NWHI bottomfish fishery from Category III to Category II due to concerns for potential interactions between bottomfish 

fishing vessels and Hawaiian monk seals, although there were none observed during 26 NWHI bottomfish trips during 

1990-1993, and none reported. On 12 of the 26 trips, bottlenose dolphins have been observed stealing fish from the lines, 

but not hookings or entanglements occurred. Effort in this fishery increases significantly around the Christmas season 

because a target species, a true snapper, is typically sought for cultural festivities.11 No data is collected for recreational or 

subsistence fishermen, but their MHI catch is estimated to be about equal to the MHI commercial catch. 

Category III, Hawaii tuna handline and jig fishery.

In 1997 a total of 543 fishers made 6,627 trips in the MHI and caught 2,014,656 pounds and sold 1,958,759 

pounds for an ex-vessel value of $3,788,391. This fishery occurs around offshore fish aggregating devices and mid-ocean 

seamounts and pinnacles. The principal catches are small to medium sized bigeye, yellowfin and albacore tuna. There are 

several types of handline methods in the Hawaiian fisheries. Baited lines with chum are used in day fishing operations 

(palu-ahi), another version uses squid as bait during night operations (ika-shibi), and an operation called “danglers” uses 

multiple lines with artificial lures suspended or dangled over the water. Interactions have been documented for roughtoothed dolphin, bottlenose dolphin, and Hawaiian monk seal. 

302
Revised 05/15/2006 Appendix 1. Description of U.S. Commercial Fisheries 

Table 1. The number of animals injured and/or killed reported to the Marine Mammal Authorization Program (MMAP) compfrom the NMFS Observer Program for the California large mesh drift gillnet swordfish fishery between 2000-2004. The drift g

observer coverage during this period. 

MMAP NMFS MMAP NMFS MMAP NMFS MMAP NMFS 

SpeciesGray whale - - - - - - - - Humpback whale - - - - - - - - Short-finned pilot whale - - - - - - - 1 Pacific white-sided dolphin 11 2 - 2 - 1 - - Bottlenose dolphin - - 1 - - - - Common dolphin spp. 17 25 7 7 4 11 7 17 Risso's dolphin 2 - - - - - - 4 Northern right whale dolphin 4 - 1 5 2 2 0 1 Unidentified small cetacean 2 - 4 - 2 - 2 - California sea lion 13 13 3 2 16 18 4 4 Steller's sea lion - - - - - - - - Northern elephant seal 2 6 - 1 - 1 - 1 Unidentified seal 1 - - - - - - - Unidentified sea lion - - - - 1 - - - Unidentified baleen whale - - - - - - - 1 Total Occurrences Reported 52 46 16 17 25 33 13 29 

2000 2001 2002 2003 

303
Revised 05/15/2006 Appendix 1. Description of U.S. Commercial Fisheries 

Table 2. Strandings reported to the NMFS Marine Mammal Stranding Network 2000-2004. hr = human-related strandings. 

Species

CA hr OR/WA hr CA hr OR/WA hr CA hr OR/WA hr CA hr OR/WA hr 

Harbor Porpoise 20 2 6 1 12 4 15 1 20 5 0 0 19 0 34 1 Dall's Porpoise 3 0 9 1 2 1 6 0 3 0 0 0 4 1 6 0 Pac. White-sided Dolphin 3 0 0 0 6 2 0 0 1 0 1 0 1 0 1 0 Risso's Dolphin 6 0 1 0 3 0 0 0 4 2 0 0 5 1 0 0 Bottlenose Dolphin 12 0 0 0 14 0 0 0 12 0 0 0 9 1 0 0 Common Dolphin (unidentified) 30 1 0 0 33 3 0 0 41 1 0 0 56 1 0 0 Short-beaked common dolphin 0 0 0 0 0 0 0 0 8 0 0 0 10 0 0 0 Long-beaked common dolphin 0 0 0 0 0 1 0 0 45 3 0 0 62 3 0 0 Striped Dolphin 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 N. Right Whale Dolphin 0 0 0 0 5 0 0 0 1 0 0 0 4 0 0 0 Rough-toothed Dolphin 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 Killer Whale 0 0 0 0 0 0 1 0 0 0 0 0 0 0 0 0 Short-finned Pilot Whale 1 0 0 0 0 0 0 0 0 0 1 0 0 0 0 0 Baird's Beaked Whale 0 0 0 0 0 0 0 0 0 0 0 0 1 0 2 1 Stejneger's Beaked Whale 0 0 0 0 0 0 2 0 0 0 0 0 0 0 0 0 Cuvier's Beaked Whale 1 0 0 0 0 0 1 1 3 0 0 0 0 0 0 0 Peruvian Beaked Whale 0 0 0 0 1 0 0 0 0 0 0 0 0 0 0 0 Unident. Beaked Whale 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 0 Unidentified Kogia 0 0 0 0 0 0 0 0 0 0 0 0 1 0 0 0 Pygmy Sperm Whale 0 0 0 0 1 0 0 0 3 1 0 0 1 0 0 0 Dwarf Sperm Whale 1 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 Sperm Whale 0 0 1 0 0 0 0 0 0 0 2 0 2 0 1 0 Gray Whale 58 8 25 0 5 1 1 0 7 3 1 1 8 3 5 1 Minke Whale 0 0 0 0 1 0 0 0 1 0 0 0 0 0 1 0 Blue Whale 0 0 0 0 0 0 0 0 3 1 0 0 1 1 0 0 Fin Whale 0 0 0 0 1 1 0 0 0 0 4 4 2 0 0 0 Sei Whale 0 0 0 0 0 0 0 0 0 0 0 0 0 0 1 1 Humpback Whale 4 3 0 0 2 1 0 0 1 0 0 0 2 5 0 0 Unidentified Cetacean 1 0 4 1 0 0 0 0 3 0 1 0 6 0 0 0 Unidentified Porpoise 0 0 0 0 0 0 0 0 0 0 0 0 0 0 2 0 Unidentified Dolphin 11 0 2 0 9 0 2 0 29 1 0 0 17 0 2 0 Unidentified Whale 1 0 0 0 4 4 0 0 2 2 0 0 1 0 1 0 Unident. Balaenopterid 0 0 0 0 2 0 0 0 2 1 0 0 0 0 0 0 Northern Fur Seal 3 0 6 0 2 0 1 1 11 0 0 0 5 0 3 2 Guadalupe Fur Seal 1 0 0 0 3 1 0 0 1 0 0 0 5 0 0 0 Steller (Nthn) Sea Lion 10 2 5 0 9 0 4 0 6 0 3 0 9 0 16 0 California Sea Lion 1268 67 32 5 990 98 27 1 1951 195 8 0 2951 184 51 4 Unidentified Sea Lion 1 0 8 0 0 0 17 0 1 0 0 0 0 0 16 1 Unidentified Otariid 0 0 0 0 0 0 0 0 2 0 0 0 1 0 0 0 Harbor Seal 230 13 148 8 152 8 170 8 163 18 121 6 211 18 211 7 Northern Elephant Seal 211 3 11 0 216 4 11 0 176 7 0 0 299 5 6 0 Unidentified Seal 0 0 17 1 0 0 11 1 1 0 0 0 0 0 0 0 Unidentified Pinniped 133 0 8 0 110 0 9 0 291 0 4 0 136 0 45 2 Totals for Cetaceans 152 14 48 3 101 18 28 2 189 20 10 5 212 16 58 4 Totals for Pinnipeds 1857 85 235 14 1482 111 250 11 2603 220 136 6 3617 207 348 16 

2000 2001 2002 2003 

304
Revised 05/15/2006 Appendix 1. Description of U.S. Commercial Fisheries 

Table 3. Characteristics of Category I and Category II gillnet fisheries in California. Fishery Species Mesh Size Water Depth Set Duration Deployment Category I CA/OR thresher shark/swordfish drift gillnet fishery 

swordfish/shark 14 to 22 inches Ranges from 90 to 

4600 meters 

Typically 8 to 15 hrs 

Drift net only 

Halibut/angel shark 8.5 inch < 70 meters 24 hrs Set net Barracuda 3.5 inch < 12 hrs Drift net Leopard Shark 7.0 to 9.0 inch < 90 meters Perch/Croaker 3.5 to 4.0 inch < 40 meters < 24 hrs Set net Rockfish 4.5 to 7.5 inch > 90 meters 12 to 18 hrs Set net Soupfin shark 6.0 to 8.5 inch > 50 meters 24 hrs Set net 

Category I CA angel shark/halibut and other species set gillnet fishery (>3.5 inch mesh) 

Miscellaneous shark 6.0 to 14 inch < 70 meters 8 to 24 hrs Drift, some set ne

Category II CA Yellowtail, barracuda, white seabass, and tuna drift gillnet fishery 

White seabass, yellowtail, barracuda, white seabass, and tuna 

Typically 6.5 inch 15 to 90 meters 8 to 24 hrs Mostly drift net 

305
Revised 05/15/2006 Appendix 1. Description of U.S. Commercial Fisheries 

Figure 1. Locations of 7,660 sets observed in the California/Oregon large-mesh drift gillnet fishery for thresher shark and 

swordfish, 1990- January 2006. The cross-hatched area has been closed to gillnetting from 15 August to 15 November 

each year since 2001 to protect leatherback turtles. The outer dashed line represents the U.S. Exclusive Economic Zone. 

Total estimates of fishing effort over this period are approximately 48,000 sets.

306
Revised 05/15/2006 Appendix 1. Description of U.S. Commercial Fisheries 

CA drift gillnet fishery for thresher 

shark/swordfish

21% 21% 20%

16%

18%

13%

14% 10%

4%

23% 20% 22%

20%

12% 23%18%

0

1000

2000

3000

4000

5000

6000

1990199119921993199419951996199719981999200020012002200320042005

Year

Effort (days)

Figure 2. Estimated (gray) and observed (black) days of fishing effort for 1990-2005 in the California/Oregon thresher 

shark/swordfish drift gillnet fishery (≥ 14 inch mesh). One fishing day is equal to one set in this fishery. Percent observer 

coverage for each year is shown above the bars. 

CA set gillnet fishery for halibut/angel shark 

8.5-inch mesh

0% 0%

5%

10%

13% 15%

8% 0% 0% 0% 0%

4% 2% 0% 0%

0

2000

4000

6000

8000

199019911992199319941995199619971998199920002001200220032004

Year

Effort (days)

Figure 3. Estimated (gray) and observed (black) days of fishing effort for 1990-2004 in the California angel shark/halibut 

set gillnet fishery (> 3.5 inch mesh). The fishery was observed only from 1990-94 and again in 1999 and 2000 in Monterey 

Bay. Percent observer coverage for each year is shown above the bars. 

307
Revised 05/15/2006 Appendix 1. Description of U.S. Commercial Fisheries 

Figure 4. Observed set locations in the Hawaii-based longline fishery, 1994-2002. 

308
Revised 11/01/2005 

Appendix 2. Cetacean Survey Effort 

This Appendix presents a summary of survey effort from which cetacean sighting locations were

plotted in the stock assessment reports. In Figures 1-6, the thick solid line represents the outer

boundary of all surveys and the thin dashed line represents the U.S. EEZ. 

Figure 1. Transect lines completed

during a 1991 winter/spring aerial survey

of California waters (Forney et al. 1995). 

Figure 2. Transect lines completed 

during a 1992 winter/spring aerial survey

of California waters (Forney et al. 1995). 

Figure 3. Transect lines completed 

during a 1991 summer/autumn vessel

survey of California waters (Barlow 

1995). 

Figure 4. Transect lines completed

during a 1993 summer/autumn vessel

survey of California waters (Mangels and 

Gerrodette 1994). 

Figure 5. Transect lines completed 

during a 1996 summer/autumn vessel

survey of California, Oregon, and

Washington waters (Barlow 1997; Von

Saunder and Barlow 1999). 

Figure 6. Transect lines completed 

during a 2001 summer/autumn vessel

survey of California, Oregon, and 

Washington waters (Appler et al. 2004). 

W132 W129 W126 W123 W120 W117

N30

N34

N38

N42

N46

WASHINGTON

OREGON

CALIFORNIA

W132 W129 W126 W123 W120 W117

N30

N34

N38

N42

N46

WASHINGTON

OREGON

CALIFORNIA

W132 W129 W126 W123 W120 W117

WASHINGTON

N46

OREGON

N42

CALIFORNIA

N38

N34

N30

W132 W129 W126 W123 W120 W117

N30

N34

N38

N42

N46

WASHINGTON

OREGON

CALIFORNIA

W132 W129 W126 W123 W120 W117

N30

N34

N38

N42

N46

WASHINGTON

OREGON

CALIFORNIA

W132 W129 W126 W123 W120 W117

WASHINGTON

N46

OREGON

N42

CALIFORNIA

N38

N34

N30

309
Revised 11/01/2005 

Appendix 2. Ce

N44

Figure 7. Harbor porpoise stock boundaries in California and southern Oregon. Stippled area shows approximate harbor porpoise habitat between 0-200 meters. Thick solid line represent surveytransects flown during 1989-2002 aerial surveys (Forney et al.1991; Forney 1995; Carretta and Forney 2004). Survey coveragenorth of the California/Oregon border has been completed by theNational Marine Mammal Laboratory (Laake et al. 1998).

Figure 8. Coastline section (in bold) suduring 1990-2000 coastal bottlenose dolphisurveys in southern and central California (Cet al. 1998, NMFS unpublished data).

W128.0 W126.0 W124.0 W122.0 W120.0 W118.0

.0 N4

N34.0N36.0N38.0N40.0N42.0 Oregon

Northe California rn California/Southern Oregon

San FranciscoRussian River

Monterey Bay

Morro Bay

Cape Blanco

Monterey Bay

Cape Mendocino

Point Conception

Point Arena

Morro Bay

Oregon/Washington coast

Russian River

W123 W122

0

N39

N38 San Francisco

N37

Monterey Bay California

N36

N35

Point Conception

N34 Los Angeles

Pacific Ocean

N33 San 

N32

N31

W121 W120 W119 W118 W117 

310
Revised 11/01/2005 

Appendix 2. Ce

Figure 9. Transect lines completed during a 2002 summer/autumn vessel survey of Hawaiian waters (Barlow et al. 2004). Thick outer survey boundary line represents the U.S. EEZ and the inner thick line represents a separate ‘Main Hawaiian Islands’ stratum. Thin lines represent completedtransect lines.

161 160 159 158 15

W Longitude

1920212223

N Latitude

Figure 10. Small research vessel survey lines comHawaiian Islands between 2000-2004 (Baird et al. 2005km of survey tracks are shown. 

N3

W180 W175 W170 W165 W160 W155 W150

N10N15N20N25N30

5

311
Revised 11/01/2005 

Appendix 2. Ce

161 160 159 158 157 156 155

W Longitude

1920212223

N Latitude

Figure 11. Aerial survey effort conducted around the Main Hawaiian Islands 

from 1993-2003 (Mobley et al. 2000, Mobley 2001, 2002, 2003, 2004). 

312
Revised 11/01/2005 

Appendix 2. Cetacean Survey Effort 

References 

Appler, J., J. Barlow, and S. Rankin, 2004. Marine mammal data collected during the Oregon, California and 

Washington line-transect expedition (ORCAWALE) conducted aboard the NOAA ships McARTHUR and 

DAVID STARR JORDAN, July - December 2001. NOAA Techinal Memorandum NOAA-TM-NMFSSWFSC-359. 32p. 

Baird, R.W., A.M. Gorgone, D.L. Webster, D.J. McSweeney, J.W. Durban, A.D. Ligon, D.R. Salden, and M.H. 

Deakos. 2005. False killer whales around the Main Hawaiian Islands: An assessment of inter-island 

movements and population size using individual photo-identification. Contract Report JJ133F04SE0120 

prepared for the Pacific Islands Fisheries Science Center, National Marine Fisheries Service, 2570 Dole 

Street, Honolulu, Hawaii, 96822. 24pp. 

Barlow, J. 1995. The abundance of cetaceans in California waters. Part I: Ship surveys in summer and fall of 1991. 

Fish. Bull. 93:1-14. 

Barlow, J. 1997. Preliminary estimates of cetacean abundance off California, Oregon, and Washington based on a 

1996 ship survey and comparisons of passing and closing modes. Admin. Rep. LJ-97-11. Southwest 

Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La Jolla, CA 92038. 25 pp. 

Barlow, J., S. Rankin, E. Zele, and J. Appler. 2004. Marine mammal data collected during the Hawaiian Islands 

Cetacean and Ecosystem Assessment Survey (HICEAS) conducted aboard the NOAA ships McArthur and 

David Starr Jordan, July - December 2002. U.S. Department of Commerce, NOAA Technical 

Memorandum, NMFS-SWFSC-362. 39 p. 

Carretta, J. V., K. A. Forney, and J. L. Laake. 1998. Abundance of southern California coastal bottlenose dolphins 

estimated from tandem aerial surveys. Mar. Mamm. Sci. 14(3):655-675. 

Carretta, J.V. and K.A. Forney. 2004. Preliminary estimates of harbor porpoise abundance in California from 1999 

and 2002 aerial surveys. SWFSC Administrative Report LJ-04-01, available from Southwest Fisheries 

Science Center, 8604 La Jolla Shores Drive, La Jolla, CA, USA. 13pp. 

Forney, K.A., D. Hanan, and J. Barlow. 1991. Detecting trends in harbor porpoise abundance from aerial surveys 

using analysis of covariance. Fish. Bull. 89:367-377. 

Forney, K.A. 1995. A decline in the abundance of harbor porpoise, Phocoena phocoena, in nearshore waters off 

California, 1986-93. Fish. Bull. 93(4):741-748. 

Forney, K.A., J. Barlow, and J.V. Carretta. 1995. The abundance of cetaceans in California waters. Part II: Aerial 

surveys in winter and spring of 1991 and 1992. Fish. Bull. 93(4):15-26. 

Laake, J., J. Calambokidis, S. Osmek. 1998. Survey report for the 1997 aerial surveys for harbor porpoise and other 

marine mammals of Oregon, Washington, and British Columbia outside waters. Alaska Fisheries Science 

Center Processed Report 98-10. pp. 77-97. 

Mangels, K.F. and T. Gerrodette. 1994. Report of cetacean sightings during a marine mammal survey in the eastern 

Pacific Ocean and the Gulf of California aboard the NOAA ships McArthur and David Starr Jordan July 28 

_ November 6, 1993. U.S. Dep. Commer., NOAA Tech. Memo. NMFS_SWFSC_221. 88 pp. 

Mobley, J.R., Jr, S. S. Spitz, K. A. Forney, R. A. Grotefendt, and P. H. Forestall. 2000. Distribution and abundance 

of odontocete species in Hawaiian waters: preliminary results of 1993-98 aerial surveys Admin. Rep. LJ00-14C. Southwest Fisheries Science Center, National Marine Fisheries Service, P.O. Box 271, La Jolla, 

CA 92038. 26 pp. 

Mobley, J.R. 2001. Results of 2001 aerial surveys north of Kauai. Report to North Pacific Acoustic Laboratory 

program. 20 pp. Available as downloadable pdf file at: 

http://socrates.uhwo.hawaii.edu/SocialSci/jmobley/2001NPAL.pdf 

Mobley, J.R. 2002. Results of 2002 aerial surveys north of Kauai. Report to North Pacific Acoustics Laboratory 

program. 20 pp. Available as downloadable pdf file at: 

http://socrates.uhwo.hawaii.edu/SocialSci/jmobley/2002NPAL.pdf 

Mobley, J.R. 2003. Results of 2003 aerial surveys north of Kauai. Report to North Pacific Acoustics Laboratory 

program. 20 pp. Available as downloadable pdf file at: 

http://socrates.uhwo.hawaii.edu/SocialSci/jmobley/2003NPAL.pdf 

Mobley, J.R. 2004. Results of 2004 aerial surveys north of Kauai. Report to North Pacific Acoustics Laboratory 

program. 25 pp. Available as downloadable pdf file at: 

http://socrates.uhwo.hawaii.edu/SocialSci/jmobley/2004NPAL.pdf

313
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Appendix 2. Cetacean Survey Effort 

Von Saunder, A. and J. Barlow. 1999. A report of the Oregon, California, and Washington line-transect experiment 

(ORCAWALE) conducted in west coast waters during summer/fall 1996. U.S. Dep. Commer., NOAA 

Tech. Memo. NMFS_SWFSC_264. 49 pp.

314
Appendix 3. 2007 Pacific Marine Mammal Stock Assessment Reports summary. Total Annual Annual Fishery

Mortality Mortality

NMFS + Serious + Serious Strategic 

Species Stock Area Center N est CV N est N min R max Fr PBR Injury Injury Status 

California sea lion U.S. SWC 238,000 n/a 141,842 0.12 1 8,511 ≥232 ≥159 N 

Harbor seal California SWC 34,233 n/a 31,600 0.12 1 1,896 ≥389 389 N 

Harbor seal Oregon/Washington Coast AKC 24,732 0.12 22,380 0.12 1 1,343 ≥15.2 ≥13 N Harbor seal Washington Inland Waters AKC 14,612 0.15 12,844 0.12 1 771 ≥34 ≥30 N 

Northern Elephant Seal California breeding SWC 124,000 n/a 74,913 0.117 1 4,382 ≥10.4 ≥8.8 N 

Guadalupe Fur Seal Mexico to California SWC 7,408 n/a 3,028 0.12 0.5 91 0 0 Y 

Northern Fur Seal San Miguel Island AKC 9,424 n/a 5,096 0.086 1 219 ≥1.0 ≥1.0 N 

Monk Seal Hawaii PIC 1,247 n/a 1,214 0.07 0.1 undet unk unk Y 

Harbor porpoise Morro Bay SWC 1,656 0.39 1,206 0.04 0.4 10 4.5 4.5 N Harbor porpoise Monterey Bay SWC 1,613 0.42 1,149 0.04 0.45 10 9.5 9.5 N Harbor porpoise San Francisco – Russian River SWC 8,521 0.38 6,254 0.04 0.5 63 ≥0.8 ≥0.8 N 

Harbor porpoise Northern CA/Southern OR SWC 17,763 0.39 12,940 0.04 1 259 ≥0 ≥0 N 

Harbor porpoise Oregon/Washington Coast AKC 37,745 0.38 27,705 0.04 0.5 277 0.6 0.6 N Harbor porpoise Washington Inland Waters AKC 10,682 0.38 7,841 0.04 0.4 63 15.2 15.4 N 

Dall’s porpoise California/Oregon/Washington SWC 57,549 0.34 43,425 0.04 0.4 347 1.8 1.4 N 

Pacific white-sided dolphin California/Oregon/Washington SWC 25,233 0.25 20,441 0.04 0.45 184 5.6 5.6 N 

Risso’s dolphin California/Oregon/Washington SWC 12,093 0.24 9,947 0.04 0.4 80 6.6 6.6 N 

Bottlenose dolphin California Coastal SWC 323 0.13 290 0.04 0.5 2.4 0.4 0.4 N Bottlenose dolphin California/Oregon/Washington Offshore SWC 3,257 0.43 2,295 0.04 0.5 23 0.2 0.2 N 

Striped dolphin California/Oregon/Washington SWC 23,883 0.44 16,737 0.04 0.5 167 0 0 N 

Common dolphin, short-beaked California/Oregon/Washington SWC 487,622 0.26 392,687 0.04 0.5 3,927 59 59 N 

Common dolphin, long-beaked California/Oregon/Washington SWC 1,893 0.65 1,152 0.04 0.48 11 12.5 12.5 Y 

Northern right whale dolphin California/Oregon/Washington SWC 15,305 0.32 11,754 0.04 0.48 113 18 18 N 

Killer whale Eastern North Pacific Offshore SWC 422 0.29 331 0.04 0.5 3.3 0 0 N Killer whale Eastern North Pacific Southern Resident AKC 89 und 89 0.04 0.1 0.18 0.2 0 Y 

Short-finned pilot whale California/Oregon/Washington SWC 245 0.97 123 0.04 0.4 0.98 1 1 Y 

Baird’s beaked whale California/Oregon/Washington SWC 313 0.55 203 0.04 0.5 2.0 0.2 0 N 

Mesoplodont beaked whales California/Oregon/Washington SWC 1,024 0.77 576 0.04 0.5 5.7 0 0 N 

Cuvier’s beaked whale California/Oregon/Washington SWC 2,171 0.75 1,234 0.04 0.4 10 ≥0.2 0 N 

Pygmy Sperm whale California/Oregon/Washington SWC unk unk unk 0.04 0.5 undet 0.2 0 N 

Dwarf sperm whale California/Oregon/Washington SWC unk unk unk 0.04 0.5 undet 0 0 N 

Sperm whale California/Oregon/Washington SWC 2,265 0.34 1,719 0.04 0.1 3.4 0.2 0.2 Y 

Humpback whale California/Oregon/Washington SWC 1,396 0.15 1,236 0.08 0.1 2.5 ≥2.2 ≥ 1.8 Y 

Blue whale Eastern North Pacific SWC 1,186 0.19 1,005 0.04 0.1 1.0 0.6 0 Y 

Fin whale California/Oregon/Washington SWC 3,454 0.27 2,760 0.04 0.3 16 1.4 0 Y 

Bryde’s whale California/Oregon/Washington SWC unk unk unk 0.04 0.5 undet 0 0 N 

Sei whale Eastern North Pacific SWC 43 0.61 27 0.04 0.1 0.05 0 0 Y 

Minke whale California/Oregon/Washington SWC 898 0.65 544 0.04 0.5 5.4 0 0 N 

unk = unknown; undet = undetermined; n/a = not applicable

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Appendix 3. 2007 Pacific Marine Mammal Stock Assessment Reports summary.

Total Annual

Annual Fishery

Mortality Mortality

NMFS + Serious + Serious Strategic 

Species Stock Area Center N est CV N est N min R max Fr PBR Injury Injury Status 

Rough-toothed dolphin Hawaii SWC 19,904 0.52 13,184 0.04 0.5 132 unk unk N 

Risso’s dolphin Hawaii SWC 2,351 0.65 1,426 0.04 0.5 14 unk unk N 

Bottlenose dolphin Hawaii SWC 3,263 0.6 2,046 0.04 0.5 20 ≥0.2 ≥0.2 N 

Pantropical spotted dolphin Hawaii SWC 10,260 0.41 7,362 0.04 0.5 74 ≥0.8 ≥0.8 N 

Spinner dolphin Hawaii SWC 2,805 0.66 1,691 0.04 0.5 17 0 0 N 

Striped dolphin Hawaii SWC 10,385 0.48 7,078 0.04 0.5 71 unk unk N 

Fraser’s dolphin Hawaii SWC 16,836 1.11 7,917 0.04 0.5 79 unk unk N 

Melon-headed whale Hawaii SWC 2,947 1.11 1,386 0.04 0.5 14 unk unk N 

Pygmy killer whale Hawaii SWC 817 1.12 382 0.04 0.5 3.8 unk unk N 

False killer whale Hawaii SWC 484 0.93 249 0.04 0.48 2.4 4.9 4.9 Y False killer whale Palmyra SWC 1,329 0.65 806 0.04 0.48 7.7 1.9 1.9 N 

Killer whale Hawaii SWC 430 0.72 250 0.04 0.5 2.5 unk unk N 

Pilot whale, short-finned Hawaii SWC 8,846 0.49 5,986 0.04 0.5 60 0.8 0.8 N 

Blainville’s beaked whale Hawaii SWC 2,138 0.77 1,204 0.04 0.4 9.6 0.8 0.8 N 

Longman's Beaked Whale Hawaii SWC 766 1.05 371 0.04 0.5 3.7 unk unk N 

Cuvier’s beaked whale Hawaii SWC 12,728 0.83 6,919 0.04 0.5 69 unk unk N 

Pygmy sperm whale Hawaii SWC 7,251 0.77 4,082 0.04 0.5 41 unk unk N 

Dwarf sperm whale Hawaii SWC 19,172 0.66 11,555 0.04 0.5 116 unk unk N 

Sperm whale Hawaii SWC 7,082 0.30 5,531 0.04 0.1 11 0 0 Y 

Blue whale Hawaii SWC unk unk 0.04 0.1 undet unk unk Y 

Fin whale Hawaii SWC 174 0.72 101 0.04 0.1 0.2 unk unk Y 

Bryde’s whale Hawaii SWC 493 0.34 373 0.04 0.5 3.7 unk unk N 

Sei whale Hawaii SWC 77 1.06 37 0.04 0.1 0.1 unk unk Y 

Minke whale Hawaii SWC unk unk 0.04 0.5 undet unk unk N 

unk = unknown; undet = undetermined; n/a = not applicable

316