Priorities for Effective

Management of Coral Diseases

Andrew W. Bruckner

U.S. Department of Commerce

National Oceanic and Atmospheric Administration

National Marine Fisheries Service

NOAA Technical Memorandum NMFS-OPR-22

August 2002

White-band disease, Acropora palmata

Black-banddisease,Stephanocoenia intersepta

White plague, White plague, Montastraea annularis Montastraea annularis
Priorities for Effective

Management of Coral Diseases

Andrew W. Bruckner

Office of Protected Resources, Rm 13604

NOAA National Marine Fisheries Service

1315 East-West Highway

Silver Spring, MD 20910-3282

NOAA Technical Memorandum

NMFS-OPR-22

August 2002

U.S. Department of Commerce

Donald L. Evans, Secretary

National Oceanic and Atmospheric Administration

Vice Admiral Conrad C. Lautenbacher, Jr., USN (Ret.)

Under Secretary for Oceans and Atmosphere

National Marine Fisheries Service

William T. Hogarth, Assistant Administrator for Fisheries
Table of Contents

EXECUTIVE SUMMARY ...................................................... 1

INTRODUCTION ............................................................. 2

INFORMATION NEEDS FOR EFFECTIVE MANAGEMENT OF CORAL DISEASES ..... 7

Early warning systems ....................... ....................... ........... 7

The spatial distribution and temporal variations of coral disease outbreaks ................ 7

Relationships with environmental factors, anthropogenic stresses and natural disturbances . . 10

Standardized nomenclature to describe, identify and differentiate diseases ............... 13

Factors that facilitate the occurrence, spread and transmission of pathogens .............. 14

Effects on population dynamics, community structure and ecosystem function ............ 16

Measures to mitigate disease impacts ....................... ..................... 19

PROPOSED STRATEGIES TO ADDRESS MANAGEMENT NEEDS FOR CORAL

DISEASES ............................................................ 20

Early warning systems ....................... ....................... .......... 20

The spatial distribution and temporal variations of coral disease outbreaks ............... 21

Relationships with environmental factors, anthropogenic stresses and natural disturbances

....................... ....................... ...................... 23

Standardized nomenclature to describe, identify and differentiate diseases ............... 24

Factors that facilitate the occurrence, spread and transmission of pathogens .............. 26

Effects on population dynamics, community structure and ecosystem function ............ 26

Measures to mitigate disease impacts ....................... ..................... 27

CONCLUSION .............................................................. 27

ACKNOWLEDGMENTS ...................................................... 29

APPENDIX I: Monitoring and Assessment Approaches .............................. 30

Atlantic and Gulf Rapid Reef Assessment (AGRRA) ....................... ......... 30

Caribbean Coastal and Marine Productivity Network (CARICOMP) .................... 33

EPA Florida Keys ....................... ....................... .............. 37

APPENDIX II. Priorities for research on coral diseases linked to management objectives in

Florida. ............................................................... 40

CORAL DISEASE LITERATURE ............................................... 41
Priorities for Effective Management of Coral Diseases

EXECUTIVE SUMMARY

Diseases and syndromes of scleractinian corals and associated species have increased in

number in recent years, and they are now recognized as important phenomena capable of altering

the structure and composition of coral reefs. Since the early 1990s there has been a concerted

effort to characterize coral diseases, including the application of novel molecular tools to confirm

identities of pathogens and understand mechanisms of host response and resistence. Most of the

causative agents of emerging diseases, factors contributing to their occurrence and spread, and

consequences on coral populations remain incompletely understood, however. A long-term,

multidisciplinary research and monitoring program for coral diseases is necessary to assist

resource managers in identifying and responding to emerging coral diseases. These efforts should

involve management-driven strategies that include 1) an early warning system to predict and

identify disease outbreaks; 2) documentation of spatial distribution and temporal variations of

coral diseases at local to global scales; 3) elucidation of relationships of environmental stressors,

localized anthropogenic impacts, and widespread phenomena such as global warming and El

Niño on coral health, disease, degradation and recovery; 4) development of standardized

terminology for diseases through characterization of the visual appearance, pathology and

etiology; 5) development of molecular probes and other tools to identify and verify microbial

pathogens in the field; 6) identification of factors that facilitate the introduction, spread and

transmission of pathogens; 7) long-term monitoring and targeted research on the effects of

disease on coral species and populations, associated species, and ecosystem structure and

function; and 8) implementation of measures to mitigate disease impacts, including strategies

that reduce anthropogenic stressors responsible for the proliferation or spread of diseases and the

development of novel techniques to treat affected corals and improve habitat quality. Progress in

coral disease research has been hindered by a lack of coordinated research, practical difficulties

in correctly identifying diseases and characterizing their etiology and epizootiology, limited

availability of funding, and limited awareness and recognition by policy makers and the public of

the importance of coral diseases and their potential global implications. Given existing

limitations in funding, disease research should be focused towards those efforts that have the

greatest management benefits with applications on local to regional scales.
2

INTRODUCTION

Coral reef ecosystems are being degraded at an accelerated rate. The underlying causes of reef

decline are diverse, and include pollution, sedimentation, fishing impacts, habitat destruction, invasive

species, bleaching, disease, global climate change, and other factors. In recent years, disease outbreaks

have caused widespread mortalities to scleractinian corals, gorgonians, sea urchins, reef fishes, sponges,

algae, and other coral reef organisms (Peters, 1997; Harvell et al., 1999; Williams and Bunkley-Williams,

2000). Characterization of the cause, prevalence, and consequences of most of these events is limited or

non-existent. For instance, hundreds of studies have been published on coral diseases (Appendix III)

since the first reported coral disease (Antonius, 1973), and yet the causative agent has been confirmed for

only four diseases (Richardson, 1998; Patterson et al., 2002). In addition, very limited quantitative data

are available on the spatial and temporal distribution of coral diseases, synergistic and cumulative effects

of environmental and anthropogenic stressors, and long-term consequences on the composition, structure

and function of reef communities (Green and Bruckner, 2000). 

Although quantitative field observations on coral diseases are restricted to a few locations and

relatively small numbers of corals, there is a growing consensus that coral diseases have proliferated in

the 1990s (Santavy and Peters, 1997; Goreau et al., 1998; Hayes and Goreau, 1998; Richardson, 1998;

Harvell et al., 1999; Williams and Bunkley-Williams, 2000). In an examination of all information

published on coral diseases between 1973-1999, diseases were reported in over 102 coral species from 54

countries, with a disproportionate number of records (66%) from the Wider Caribbean (Green and

Bruckner, 2000). Currently, the majority of these reports are for black-band disease (BBD), white-band

disease (WBD) and white plague. These diseases were first documented from the wider Caribbean in the

1970s, but they were reported at a low prevalence or from few locations (Antonius, 1977; Garrett and

Ducklow, 1975; Dustan, 1977). Outbreaks of BBD and WBD were reported from numerous locations in

the Caribbean in the 1980s and 1990s, and both are now circumtropical in distribution (Antonius, 1987;

Green and Bruckner, 2000). White plague was first identified as a significant infectious disease in the

Florida Keys in 1975, and it was still common in 1984 on 19 different reefs in the Key Largo region

(Dustan, 1977; 1993). A more virulent form of white plague (plague type II) emerged in 1995 on reefs in

the northern Florida Keys (Richardson et al., 1998a,b). Additional outbreaks of white plague (plague type

II and type III) were also observed in Florida and other locations around the Caribbean between 1999-

2001 (Weil, 2001; Nugues, 2002; Miller et al., in press; Richardson and Aronson, in press; Bruckner,

unpubl. Obs). To date, 27 other diseases of scleractinian corals and gorgonians were reported from the

western Atlantic (Table 1) and 16 from the IndoPacific (Table 2). Western Atlantic reefs have 
3

Table 1. Diseases, syndromes, abnormal tissue conditions, and parasitic infestations of scleractinian corals and gorgonians on

coral reefs in the tropical western Atlantic. Data are compiled from publications and web sites on coral disease identified

through 2002. Other names are used in the literature to describe similar disease signs but these have been combined under the

following diseases: (1) BBD is also called black line disease; (2) WBD and white plague are also called white line disease; (3)

WBD is also used to describe massive corals in the Caribbean with signs similar to white plague; (4) YBD is also called

yellow-band disease and yellow pox disease; (5) rapid wasting disease was renamed rapid wasting syndrome, and recently

reported to be synonymous with parrotfish white spot biting; and (6) ridge mortality has been called damselfish-ridge

denuding syndrome.

Condition First

observed

Known Range Affected spec ies Source

Black-band

disease (BBD)1

Belize; Florida;

Puerto Rico

W. Atlantic

20 countri es

faviids, agaricids

gorgonians

22 species total

Antonius, 1972

White-band

disease (WBD)2

St. Croix Aruba, Bahamas, Belize, Bonaire,

British Virgin Islands (BVI), Cuba,

Curacao, Florid a, Guadalupe,

Jamaica, Puerto Rico, Tobago,

Nicaragua, St. Lucia, US Virgin

Islands (USVI) 

A. palmata

A. cervicornis

A. prolifera

Gladfelter, 1977

WBD type II Bahamas Bahamas A. cervicornis Richie and Smith,

1995

Shut-down

reaction

Florida, Belize Belize, Florida massive corals,

acroporids

Antonius, 1977

White plague 3 Florida Bahamas, Bermu da, Bonaire, BVI,

Curaçao, Florida, Guadalupe, 

Jamaica, Nicaragua, Puerto Rico,

Tobago, St. Lucia, USVI

faviids, agaricids,

mussids, poritids; 

12 species

Dustan, 1977

Plague type II Florida Bonaire, Curaçao, Dominica,

Florida, Mexico, Puerto Rico, St.

Lucia, USVI, Venezuela

 

33 species

Zorpette, 1995

Plague type III Florida Caribbean large massive corals (M.

faveolata, C. natans) 

Richardson and

Aronson, 2001

Yellow-blotch

disease (YBD)4

Florida Bahamas, Bonaire, Curaçao,

Dominica, Florida, Honduras,

Jamaica, Mexico, Panama, Puerto

Rico, St. Lucia, Venezuela

Montastraea annularis

complex; C. natans

Reeves, 1994

White pox Florida Bahamas, Florida A. palmata Porter, 1996

Patchy nec rosis Puerto Rico Caribbean A. palmata Bruckner and

Bruckner, 1997

Rapid wasting

disease 5

Bonaire Caribbean Montastraea spp., 

C. natans

Cervino et al., 1997

White spot

syndrome

Caribbean ? massive corals Global Coral Reef

Alliance web pages

(Cervino, pers. comm)

Ridge mo rtality 6 Flower Gardens,

Gulf of Mexico

Caribbean C. natans, 

D. strigosa

Abbott, 1979

Dark-spo ts

disease (DSD)

Columbia Caribbean M. Annularis, S. siderea, 

S. radians, S. intersepta

Gil-Agudelo and

Garzón-Ferreira, 2001
4

Table.1 continued . Diseases, synd romes, abnormal tissue conditions, and parasitic infestations of scleractinian co rals

and gorgonians in the trop ical western Atlantic continued. ** Mo rtalities of sea fans were observed in the 198 0s,

but they may be caused b y disease or other factors.

DSD- II Bermuda,

Bonaire,

Colombia, Puerto

Rico and

Venezuela

Caribbean S. intersepta; M.

annularis; M. faveolata;

M. cavernosa; C.

natans; C. amaranthus;

S. siderea

Weil, 2001

Red-band d isease

(RBD) type I

Belize,Jamaica

Puerto Rico

Belize, Curaçao, Dominica, Jamaica

Puerto Rico

Gorgonia, Agaricia,

Colpophyllia,

Mycetophyllia and

Stephanocoenia

Rützler et al., 1983

Santavy and Peters,

1997

RBD type II Bahamas Bahamas D. stigosa, M. annularis,

M. cavernosa, P.

astreoides and S. radians

Richardson, 1992

Hyperp lasia Puerto Rico, US

Virgin Islands,

Jamaica,

Netherlands

Antilles, Trinidad,

Belize

Caribbean massive corals Loya et al., 1984

Neoplasia Florida Florida, Netherlands Antilles,

Puerto Rico, Trinidad

A. palmata Peters et al., 1986

Coccid iosis Jamaica, Puerto

Rico, USVI 

A. agaricites, D.

cylindicus, D. strigosa,

M. meandrites, M.

cavernosa, P. astreoides,

P. porites 8 species

Upton and Peters,

1986

Nematopsis spores USVI Porites spp. Peters, 1984

Stress-related

necrosis

Puerto Rico Peters, 1984

Ring disease Bermuda Florida, Honduras D. labyrinthiformis Weil, 2001

Finger coral

denuding

syndrome

? Porites porites Williams and

Bunkley-Williams,

2000

Star coral p olyp

necrosis

? M. cavernosa Williams and

Bunkley-Williams,

2000

Algal tumors Bonaire, Trinidad Caribbean Gorgonia spp.

Pseudoplexaura;

Plexaura

Morse et al., 1977

Aspergillo sis Columbia, Costa

Rica, Panama,

Trinidad**

Caribbean Gorgonia spp. Nagelkerken et al.,

1997

Fire coral fungal

disease

Florida Florida Millepora spp. TeStrake et al., 1988
5

Table 2. Diseases, syndromes, and anomalies reported to affect stony corals in the tropical Pacific Ocean, Indian

Ocean and Red Sea.

Condition Location Species affected Source

Black-band d isease Australia, Egypt, Fiji,

India, Papua New Guinea,

Philippines, Saudi Arabia 

Tonga, United Arab

Emirates

Favia, Favites, Acropora,

Montipora, Pachyseris,

Platygyra, Goniastrea,

Leptoria, Turbinaria,

Montastraea, Hydnophora

20 species

Antonius, 1987; Chesher, 1984

Glazebrook and Steiner, 1994

Littler and Littler, 1995

Miller, 1996

Korrubel and Riegl, 1998

Fenner, 1998; Cervino, 1998

White-band d isease Australia, Egypt,

Fahl Island, Guam,

India, Mauritius, Oman,

Papua New Guinea,

Philippines, Saudi Arabia,

United Arab Emirates

Acropora, Goniastrea

Platygyra, Hydnophora

Leptoria, Favia, Pocillopora,

Stylophora,Lobophyllia,

Porites, Leptoseris,

Echinopora, Mycedium,

Podabacia, Monitopora,

Symphyllia 33 species

Antonius, 1987

Coles, 1994

Korrubel and Riegl, 1998

Shutdown reaction Saudi Arabia, Tonga Acropora Antonius, 1981

Chesher, 1984

White blotch disea se Australia Acropora Dinsedale, 1994

Brown-band disease Australia Acropora Dinsedale, 1994

Black aggressive band Mauritius Acropora Antonius, 1995a

Black overgrowing

cyanoba cteria

Indian Ocean Acropora, Pocillopora,

Porites, Favia

Antonius, 1995a

Halofolliculina

corallasia , ciliate

Antonius, 1999

Skeleton eroding band Egypt massive corals Antonius, 1999

Pink line disease Papua New Guinea,

Sri Lanka

Porites Goreau/Cervino, coral list

server

Yellow-band d isease United Arab Emirates;

Arabian Gulf

Acropora, Porites,

Cyphastrea, Turbinaria

10 species

Korrubel and Riegl, 1998

Fungal infection Adaman Islands, Indian

Ocean

Porites, massive corals Raghukumar and Raghukumar,

1991; Ravindran et al., 2001

Porites ulcerative

white spot disease

Philippines Porites Raymundo and Harvell, 2000

Tumors

(calicoblastic

epitheliomas)

Australia (GBR), Indian

Ocean, Hawaii, Guam,

Enewatak, French

Polynesia, Gulf of Oman

Platygyra;

8 families; most common in

Acropora

Loya et al. 1984

Glazebrook and Steiner, 1994

Coles and Seapy, 1998

Pink-blue disease Israel Acropora, Porites Red Sea Marine Park, 2001

Rapid tissue necrosis Aquarium Corals Acropora, Pocillopora,

Seriatopora ; 11 others

Borneman, 2001
1Epizootiology is the science that deals with outbreaks of animal diseases, including the prevalence and

variability at local, regional and temporal scales, factors involved in the occurrence and spread, and the effect on

host populations. It is the equivalent of human epidemiology.

6

become a “hot spot” for diseases, due to increased virulence and rapid spread of pathogens, a rapidly

expanding host range of coral diseases, a recent emergence of new diseases, and the relatively small,

partially enclosed and interconnected nature of the Caribbean basin (Porter and Tougas, 2001; Goreau et

al., 1998; Hayes and Goreau, 1998).

It is now recognized that coral diseases have played an important role in the loss of coral cover

over the last two decades. For instance, there is good evidence that mortality from WBD has modified

the structure and composition of reefs in the wider Caribbean by removing two of the most common and

locally abundant species (Aronson and Precht, 2001). However, environmental perturbations and

anthropogenic stressors that may have triggered disease outbreaks or contributed to their spread and

severity are not fully understood. In addition, our ability to predict the long-term impact of emerging

syndromes and coral diseases is hindered by an incomplete understanding of 1) ecological processes and

interactions at the species, population and community level; 2) connectivity among reefs and the

importance of regional and local water movement patterns as vectors for dispersal of (coral) propagules

and water-borne pathogens; and 3) factors that influence the resilience of coral reef ecosystems and their

ability to persist under increasing environmental and anthropogenic impacts. 

While much research is needed to achieve a better understanding ecological and oceanographic

processes affecting coral reef ecosystems and responses of these ecosystems to chronic impacts, there is

also an urgency to understand the causes of diseases and their consequences on coral populations. 

Regional and global coral reef monitoring programs [ReefCheck, Caribbean Coastal Marine Productivity

(CARICOMP), Atlantic and Gulf Rapid Reef Assessment (AGRRA)] are providing valuable information

on reef condition and threats. Some of these programs also include methodologies for disease surveys

(Appendix I). However, there remains a need for targeted studies on coral disease etiology and

epizootiology1, to identify and characterize disease-causing microorganisms, and to understand processes

and stressors that may trigger outbreaks of disease and exacerbate their impacts. In addition, resource

managers need effective tools to control disease epizootics and reduce coral mortality. 

The purpose of this paper is to summarize the type of information needed by resource managers

to improve their ability to effectively manage coral diseases, and to discuss impediments hindering

progress in coral disease research. Specific examples from the literature highlight some of the existing

limitations of available data. The focus of this paper is on the use of rapid ecological assessments, longterm monitoring, and targeted research to address gaps in the understanding of coral diseases, with a
7

discussion of possible strategies to link coral disease research with management objectives. Descriptions

of regional coral disease monitoring protocols and techniques used by scientists illustrate the existing

methodologies used to characterize coral disease epizootiology (Appendix A). Priorities for management

of diseases identified by the Florida Keys National Marine Sanctuary (FKNMS) in their draft science

plan are also summarized (Appendix B).

Key priorities for effective management of coral reef diseases

1. Early warning systems

The challenge: Coral ble aching and disease ou tbreaks ma y be linked to unusual enviro nmental eve nts. Yet, it is

difficult to reliably predict their occurrence or potential impacts, or to separate the relationships of these events from

natural variations in disease occurrence.

The health of coral reef ecosystems is closely linked to physical properties of the environment

and ecological linkages among species . Certain global or regional-scale disturbances such as coral

bleaching occur during periods of elevated water temperature, high UV radiation, excessive

sedimentation and similar stressful events. Such events have been numerous in the Florida Keys

(FKNMS) and some of these have been followed one to two years later by the appearance of a disease

outbreak (B. Causey, pers. comm, Jan. 2002). However, the relative importance of large-scale

phenomena such as global warming and El Niño as a cause of coral mortality, and how much these

phenomena affect the prevalence and severity of coral diseases are unknown. By understanding the

synchronization of various stressful events and the occurrence of coral diseases, managers may be able to

predict potential threats in a timely manner and develop strategies to lessen impacts. This information

may also assist in interpreting changes in reef condition that occur in response to these events, and

separate these from natural variations. Unfortunately, the wide distribution and remote location of many

coral reefs presents challenges for in situ monitoring of unusual environmental events and their

relationships with bleaching and disease outbreaks.

2. The spatial distribution and temporal variations of coral disease outbreaks

The problem: Limited qu antitative information exists on th e prevalen ce and incid ence of dise ases. Existing d ata

may not be representa tive over large geograp hic or temp oral scales, o r even at loca l scales, due to the small samp le

sizes of corals, few reefs examined, and infrequent sampling that is characteristic of most studies.

A summary of all in situ observations (up to 1999) on the prevalence, range of species

affected, global geographic distribution, and mortality for the “major” diseases has been

compiled by Green and Bruckner (2000). This review highlights the large geographic scale over which
8

diseases have been reported, but many of the records represent qualitative observations only. Currently,

detailed quantitative data on the prevalence of diseases are available only for a few locations (e.g.,

Florida) and diseases (primarily BBD, WBD and white plague). There have been a few recent regional

studies to evaluate the health of coral reefs and the occurrence of diseases. This includes the Atlantic

and Gulf Rapid Reef Assessment (AGRRA) surveys conducted between 1998-2000 in 22 countries

(Kramer et al., in press), and a CARICOMP survey of 19 reef sites from 6 countries in the Caribbean

(Weil, in press). 

A. White-band disease (WBD)

White-band disease has been reported from most countries in the Caribbean, and it is believed to

be the major factor responsible for the regional decline of Acropora cervicornis and A. palmata (Aronson

and Precht, 2001). However, quantitative data on disease prevalence and incidence are available for few

locations, and these show large local, regional, and seasonal variations (Table 3). In addition, long-term

monitoring of WBD on relevant temporal scales was conducted only in the USVI (Gladfelter et al., 1977;

Gladfelter, 1982; Gladfelter, 1991). WBD was observed on acroporids in many other locations, and

extensive mortality occurred at some later date, but conclusive proof to verify that WBD was the leading

(or only) source of mortality is not available. Localized losses of these species have been attributed to

other factors (storms, predation, bleaching etc.), yet some authors have concluded that a new disease,

white pox, is actually the major source of mortality to A. palmata in Florida (Patterson et al., 2002). The

importance of these factors versus WBD, or their relationships with WBD have not been fully

characterized, and research should be targeted to answer these questions.

Table 3. An ex ample of the variation in prevalenc e of white-band disease rep orted during the 198 0s.

Prevalence of WBD Location Author

2-5%; up to 40% Florida, USVI, Belize Antonius, 1981

5-26% British Virgin Islands Davis et al., 1986

1-2%; up to 64% U.S. Virgin Islands Gladfelter et al., 1977

20-33% La Parguera, Puerto Rico Goenaga and Boulon, 1992

> 80% Jamaica; Netherlands Antilles Rogers, 1985

B. White plague

Studies from the Florida Keys suggest that white plague may have been a significant factor

contributing to the declines in live coral cover over the last 20 years (Dustan, 1977; Dustan and Halas,

1987; Richardson et al., 1998 a,b). Plague type II has been one of the most severe disease events in terms 
9

of the number of coral species affected, the rates of tissue loss, extent of mortality, and the rapid spread

along the Florida reef tract (Richardson and Aronson, in press). However, it is difficult to evaluate longterm impact on coral populations in Florida because the disease has not been monitored repeatedly

(weekly to monthly) over single years or continuously for multiple years (Table 4). The value of

frequent monitoring to accurately track the spread of a coral disease and evaluate its effect on coral

populations is illustrated by a study from the USVI where researchers monitored coral populations

monthly for about 4.5 years. They identified frequencies of plague type II that ranged from 3-58%, with

new infections observed each month and an absence of a seasonal correlation in disease prevalence 

(Miller et al., in press).

The examples presented in Table 4 illustrate the high percentage of stressed, diseased, and dying

corals identified in surveys, but these studies often do not distinguish between cause and effect of

mortality. For instance, Dustan and Halas (1987) identified numerous dead corals in their transects

which may have died from white plague, BBD, sediment-related tissue loss or other factors. Also,

diseased corals were identified during surveys, a decline in coral abundance was noted at a later

date, but it is not possible to verify that the identified disease was the sole cause of this decline.

Table 4 . Reports o f white plague fro m the Florid a Keys. 

Species Description of event Location Author

M. ferox, M. lamarckiana, C. natans,

M. annularis, P. astreoides, 

S. michelini 

1) Outbreak observed in 1975; 

2) Highest prevalence in M. ferox (24-73%); 

3) Spread of up to 3.1 mm/day in M. ferox; 

4) Mortality of 20-30% of M. ferox in one year.

Carysfort,

Elbow, French,

Key Largo Dry

Rocks, Molass es

Dustan, 1977

Species with pla gue not identified 1) Corals at 10 -21 m declined in abunda nce between

1974-1982;

2) Skeletons of M. ferox, M. lamarckiana, S. hyades and

C. natans recorded along transects;

3) BBD, white plague and sediment-related tissue loss

prevalent.

Carysfort Dustan and

Halas, 1987

Species with pla gue not identified 1) 362 out of 9 800 (3.69%) colonies with wh ite plague;

2) Prevalence same on all reefs (no “hot spots”).

19 reefs in Key

Largo

Dustan, 1993

A. agaricites, A. lamarcki, C. natans,

D. cylindricus, D. stokessi, 

D. labyrinthiformis, D. strigosa, 

E. fastigiata, M. decactis,M. mirabilis, 

M. areolata, M. meandrites, 

M. annularis, M. cavernosa, 

S. siderea, S. bournoni, S. michelinii

1) Outbreaks of plague type II from 1995-1997;

2) Plague type II spread throughout the Florida Reef Tract;

3) Epizootics confined to the middle keys in 1995, 

southern keys and the Dry Tortugas in 1996, and reefs

north of Miami in 1997;

4) Up to 38% mortality of one species;

5) Seasonal occurrence (June-October)

23 reefs over

200 km reef tract

Richardson et

al., 1998a

C. natans, M. faveolata Outbreaks of plague type III reported from Florida in 1999 Richardson

and Aronson,

in press
2Reefs at Risk (1998 ) presents an indicator of potential threats from coastal development, overexploitation and

destructive fishing, impact of inland pollution and erosion, and marine pollution based on a series of distance

relationships correlating mapped locations of human activity. It also considers population demography, rainfall, and

topography of assoc iated land masses.

10

There are several possible pitfalls associated with infrequent monitoring and sampling of a small number

of reefs in one location (Bruckner and Bruckner, 1997):

• Diseases often occur at a low frequency, but they may be clumped in occurrence. Surveys that are not

representative, or are too few number, may miss localized aggregations of diseased corals and

underestimate disease prevalence or they may focus on localized areas with multiple diseased corals

and overestimate disease prevalence.

• Diseases often affect individual hosts for a relatively short time, with new diseases appearing on

surrounding corals at frequent intervals. Surveys conducted infrequently are unable to accurately

assess the duration of individual diseases and their role in coral mortality.

• Some diseases exhibit seasonal variations in abundance or occurrence. Surveys conducted during

certain times of the year may incorrectly estimate disease prevalence or incidence, and the impact of

diseases.

• Coral mortality may be caused by numerous factors, in addition to disease. Infrequent surveys may

overestimate the role of disease in coral mortality, by not identifying other causes of mortality (e.g.,

injury, predation, sedimentation) and their relative importance. 

3. Relationships with environmental factors, anthropogenic stresses and natural disturbances

The problem: The recent emergence of diseases is often presumed to be related to habitat degradation,

increased human impacts, or poor water quality, but linkages with specific factors have not been

conclusively determined. Reef managers need to recognize and partition various threats that may affect

the occurrence, prevalence, or severity of diseases so their sources can be identified, and possibly

reduced through better management practices.

Although it has been difficult to identify the cause of most new diseases, the sudden emergence

may be related to deteriorating and changing environmental conditions (Santavy and Peters, 1997). For

example, eutrophication may be an important source of stress that compromises a coral’s immune system

and decreases the resistance to disease, and it may also promote proliferation of pathogens, allowing new

diseases to emerge (Hayes and Goreau, 1998). Green and Bruckner (2000) mapped the spatial

distribution of coral diseases, and noted that 97% of all locations in the Caribbean affected by coral

diseases correspond to areas where human activities are expected to have medium to high impacts, based

on the Reefs at Risk analysis2

. 

Porter and Tougas (2001) presented a coral disease stress model that links environmental quality

with incidence of disease. In this model, a variety of stresses (elevated temperature, increased storm

frequency, elevated nutrients and toxins and decreased water clarity) are predicted to suppress the
11

immune and disease defense systems in corals. The consequences of reduced health include increases in

the number of pathogenic organisms, susceptible species, locations affected by disease, and mortality

rates. The authors suggest that the model is applicable to the Florida Keys, where a dramatic increase in

the number of diseases, the number of species affected, and the rates of coral mortality were recorded in

40 sites between 1996-1998. 

A. Black-band disease

Previous studies quantifying the spatial and temporal distribution and abundance of BBD

illustrate the widespread distribution of the disease, but infections exhibit significant variations in

prevalence and dispersion (Table 5). BBD occurs on most reefs at a low abundance, although infections

may be aggregated, and outbreaks have been reported from numerous locations (Peters, 1993; Bruckner

et al., 1997). Goreau et al. (1998) report that BBD often first appears in polluted areas, and infections

spread radially outward. They suggest that the abundance of BBD mimics the distribution of human

influenced areas, with the largest impacts near sewage outflows and areas of high turbidity from eroded

soil. Peters (1993) also noted that BBD prevalence is related to adverse environmental conditions,

including warmer than normal temperatures, nutrient loading, increased sedimentation and turbidity,

predation, and toxics. Antonius (1998a) identified BBD on reefs in the Red Sea located in close

proximity to industrialized areas, with a notable absence of the disease in other locations. In Jamaica, the

incidence of BBD progressively increased over 19 months, with the largest increase during or just after a

period of unusual rainfall and run-off (Bruckner et al., 1997a). In this study, the incidence of BBD was

not correlated with run-off in the most commonly affected species (M. annularis; M. cavernosa and

Diploria spp.). However, one species that is thought to be highly resistant to BBD (S. siderea) exhibited

few infections prior to the rainfall event, with a dramatic increase in bleaching, white plague and BBD in

the second year of the study, corresponding to periods of high rainfall and run-off (Bruckner, et al.,

1997). Richardson (1995) compiled information on BBD incidence versus nutrients, temperature, light,

turbidity, salinity, coral cover, and coral diversity for 200 sites in the Florida Keys. This study may

further clarify the role of environmental quality; however, at least initially, she noted that there is no

clear correlation. 

An extensive, multi-year study conducted in Puerto Rico by Bruckner (1999) suggests that a

negative relationship may exist between BBD prevalence and turbidity or elevated nutrients. The lowest

prevalence of BBD overall was found near Mayaguez and Ponce, which are some of the most polluted

and turbid sites in Puerto Rico due to high sedimentation and nutrification associated with river

discharge, agricultural runoff, and direct input of untreated sewage. In addition, the incidence of BBD on

a fringing reef off the west coast (Rincon) was highest in spring (May-June) when water clarity was high,
12

with infections disappearing during the rainy period (July-August) when run-off increased and visibility

declined, even though temperatures were approaching their annual maxima. Furthermore, high turbidity

was one of the major factors limiting the spatial distribution of BBD in La Parguera. Infections were

restricted to shallow water on turbid inshore reefs, even though species susceptible to BBD occurred in

shallow and deep water, while BBD occurred to depths of 30 m on offshore reefs with high water clarity. 

The disease was also common in remote locations around Mona Island, which is 70 km from the

mainland of Puerto Rico and lacks permanent inhabitants, industry or agriculture (there is a small Puerto

Rico Department of Natural and Environmental Resources facility and camping is permitted) and reefs

are unaffected by river discharge (Bruckner, 1999).

Table 5. A comparison of published quantitative studies on black-band disease from the Caribbean.

Location Survey information BBD prevalence Habitat and environmental cha racters Author

USVI 22 sites on 7 reefs;

9204 corals; 4

surveys in 1 year.

0.2% of all corals; 5.5% of D.

strigosa; random dispersion; BBD

declined in November.

high density of corals (1.3 colonies/m2

) but

only 24% of all corals in study area were

susceptible to BBD; undeveloped watershed.

Edmunds,

1991

Florida 19 reefs; 9800 corals;

single survey.

6%; same prevalence on all reefs. surveys in 1980s; higher coral cover and

abundance than in the 1990s.

Dustan,

1993

Florida 10 sites on 3 reefs;

1397 corals; 3 surveys

in 1 year.

0.72%; clumped distribution;

seasonal occurrence, but some

corals infected year-round.

low density of corals (0.15 colonies/m2

);

large annual decline in temperature; possible

water quality issues.

Kuta and

Richardson,

1996

Jamaica 20 sites on 4 reefs;

5564 corals; 

bi-monthly surveys for

20 months.

5.2% total over 20 months; max

1.2% at one time; clumped

distribution; new infections during

each survey; no decline in winter,

except in M. cavernosa.

>90% of the corals in sites were susceptible

to BBD; moderate density of corals (0.9

colonies/m2); seasonal periods of high

rainfall and runoff.

Bruckner et

al., 1997a

The role of physical factors (temperature, light, wave action), anthropogenic stressors (nutrients,

sediments, pollutants) and other environmental stressors must be carefully evaluated before concrete

conclusions of relationships with disease can be made. Most coastal environments are affected by a suite

of anthropogenic inputs, making it difficult to identify any one specific cause associated with

deteriorating health or an increased prevalence of disease. Differences in prevalence, severity or impact

of diseases may be related to specific anthropogenic stressors, other biotic or abiotic parameters or

multiple factors. For instance, habitat characteristics and composition including the cover and abundance

of susceptible corals, the amount of macroalgae, or presence or absence of certain key indicator species

such as Diadema may influence coral diseases. 
13

4. Standardized nomenclature to describe, identify and differentiate diseases

The problem: Inconsistent terminology for coral diseases, absence of standard requirements for reporting of new

diseases, and lack of field identification tools hinders our ability to obtain accurate information on the types of

diseases, their prevalence, and their imp acts.

There is considerable disagreement among coral disease specialists about many of the

fundamental aspects of the newly emerging diseases. This includes a profusion of names describing socalled “new diseases” which may represent conditions caused by pathogens, predators, environmental

perturbations, or other factors (Goreau et al., 1998; Bruckner and Bruckner; 1998, Richardson, 1998). In

the majority of cases, researchers have assigned names to coral syndromes based on the appearance of

the microbial community (e.g., BBD), the color of the affected tissue (YBD), or the pattern of loss of

coral tissue (WBD). In a recent review of coral disease literature, Green and Bruckner (2000) noted that

29 different “disease states” had been reported. In some cases, a variety of similar names were used to

describe different diseases; in others, different names were used by separate researchers to describe

apparently similar disease signs. For instance, the term white-band disease (which occurs only in

Acropora spp. in the Caribbean) has been used to describe similar signs in massive and plating corals that

are reported elsewhere as white plague (Table 1). Also, similar gross signs of coral abnormalities that

are classified as the same disease have been later shown to have different histological characteristics

(Santavy and Peters, 1997). There has also been an uncertainty as to whether what is being described as a

coral disease is actually a biotic or abiotic disease, or whether it is caused by other factors. This includes

rapid wasting disease (later renamed rapid wasting syndrome), which has been shown to be the result of

focused biting by Sparisoma viride (Bruckner and Bruckner, in press), a phenomena that was

documented over 100 years ago. Another example is ridge mortality disease (Abbott, 1979), a condition

that affects brain corals and other species. This condition is always associated with Stegastes planifrons

predation and the development of algal lawns (Bruckner, 2001), and has been termed damselfish ridgedenuding syndrome by other authors (Williams and Bunkley-Williams, 2000).

In the last five years there have been numerous “review articles” on coral diseases (Cervino and

Smith, 1997 a,b; Santavy and Peters, 1997; Peters, 1997; Bruckner and Bruckner, 1997c; Richardson,

1998; Goreau et al., 1998; Hayes and Goreau, 1998; Harvell, et al., 2000; Williams and BunkleyWilliams, 2000; Borneman, 2001; Bruckner, 2001; Richardson and Aronson, in press). Many of these

provide descriptions and lists of reported diseases, but the summaries often lack a thorough review of

existing literature, and may be heavily biased towards work by one or a few researchers. In addition,

some of these articles have been published without a thorough and unbiased peer-review. In some cases,
14

these articles have discounted many of the presumed diseases, while they identify additional “new”

syndromes without any supporting quantitative field or laboratory studies. In other cases, even after

considerable supporting evidence is available that discounts a presumed disease, references to this

condition continue to appear in scientific literature and popular articles. Along with the continued

controversy regarding many of the presumed new diseases, many of the articles draw conclusions on the

recent spread, prevalence, associated factors, or potential impact based on qualitative information, in

absence of sound quantitative science. Without a coordinated and cooperative effort among all

researchers working on coral diseases, this misinformation is likely to continue to proliferate, severely

affecting our ability to respond to a growing coral reef crisis. 

5. Factors that facilitate the occurrence, spread and transmission of pathogens

The problem: The source of emerging diseases and their mode of spread and transmission is unknown.

It is currently unclear whether the recent emergence of diseases is associated with the

introduction of pathogenic organisms from terrestrial environments, or whether disease-causing microbes

have always been present but have only recently become pathogenic due to deteriorating environmental

conditions and/or reduced host resistance. A critical area of research is the identification of disease

sources and vectors, and natural reservoirs for pathogens. Possible sources include the introduction of

novel pathogens via aerosols (e.g., African dust), run-off, sewage, vessel discharge, the introduction of

exotic species as well as the movement of water masses as a vector for dispersal (NCORE, 2001). 

Black-band disease now occurs in most reef environments in the western Atlantic. In many

locations BBD increases seasonally in summer and fall, with infections becoming rare or absent during

winter when water temperatures decline (Kuta and Richardson, 1996). Factors responsible for the

reappearance the following year are not completely understood, but the occurrence of the dominant

microorganism (Phormidium corallyticum) outside of the black-band association has been reported. 

During surveys in Belize, Florida and the Bahamas, Taylor (1983) reported the occurrence of P.

corallyticum from shaded areas under reef limestone not in association with living corals. Richardson

(1997) identified non-pathogenic biofilms that contained P. corallyticum and other cyanobacteria in

sediment patches on the surface of healthy, BBD-susceptible corals. However, none of these developed

into active BBD after 12-17 months. Santavy and Peters (1997) also identified algal mats that contained

P. corallyticum filaments at the base of a reef in the Bahamas. 
15

Although P. corallyticum was not identified in plankton tows, injured colonies have become

infected with BBD when placed downstream from an infected colony, suggesting that the disease is

transmitted in the water column (Rützler and Santavy, 1983; Antonius, 1985b). In Jamaica, a BBD

epizootic was observed at the eastern end of a reef system and it progressed to the west over 20 months,

in the direction of the major water current (Bruckner et al., 1997 a). In this study, portions of the BBD

mat became dislodged during periods of high wave action, and floated towards other corals down current. 

Although the dislodged BBD mat was not observed to land on and infect a new host, a high number of

new infections were identified down-current 1 to 3 weeks after periods of high wave action (Bruckner et

al., 1997 a). While water motion provides a vector for transmission of BBD, under extreme wave

conditions, water turbulence may actually limit BBD progress and prevent new infections from becoming

established. On exposed shallow (1-2 m) reefs on the north coast of Puerto Rico, a high incidence of

BBD has been observed during spring and summer, coinciding with periods of low to moderate wave

surge. In fall, although temperatures are approaching their maximum (29°C), BBD virtually disappears

from exposed reefs; the decline corresponds to the onset of fall and winter storm waves. In certain

protected locations, BBD reaches its maximum annual abundance during this period (Bruckner, 1999).

There is the possibility that pathogenic microorganisms may be transported into coastal

environments along with soil during periods of run-off (Epstein et al., 1998). Aspergillus sydowii, a

fungus identified as the cause of aspergillosis in sea fans, is reported to be of terrestrial origin. One

hypothesis is that A. sydowii was transported to coral reef environments via run-off; however, fungal 

isolates from the terrestrial environment are not pathogenic to corals. An alternate hypothesis is that A.

sydowii was transported to Caribbean reefs in clouds of dust from western Africa (Weir et al in press).

Another new disease, white pox, has been recently characterized as being caused by a common

bacteria, Serratia marcescens (Patterson et al., 2002). These authors conclude that the bacteria is

associated with the human gut and may be introduced into the marine environment via human waste. 

However, others have noted that the bacteria is very common in the intestines of other animals, including

fish. One fish, Sparisoma viride, forms territories within areas dominated by A. palmata, and the fish will

frequently defecate as they swim over standing elkhorn coral colonies. The fecal matter will accumulate

on the surface of elkhorn branches during calm periods, and will cause mortality. It is possible that the

parrotfish are the main vector for the bacterium that causes white pox, negating the linkage with human

sewage.
16

6. Effects on population dynamics, community structure and ecosystem function

The problem: Long-term consequences of diseases on coral reefs are largely unknown. Managers need information

on the fates of corals, the resilience of coral populations, potential effects on associated species, and long-term

impacts on coral reef co mposition , structure and function. 

Hayes and Goreau (1998) concluded that mortality from coral reef diseases has the potential to

be more detrimental to the survival of coral reefs than sedimentation, pollution, physical degradation, or

all other threats combined. It is clear that coral diseases can have a major impact on the structure and

composition of coral reef ecosystems, as evidenced by the regional spread of WBD and devastating

levels of mortality to acroporid populations. However, the fates of individual colonies, the resilience of

coral populations, and the long-term effects on associated species and the ecosystem are a complex

interaction of multiple factors, of which disease may be one important factor. For instance: 

• The virulence of pathogens is likely to vary among diseases and affected species, with additional

seasonal and spatial variations and possible synergistic impacts from other disturbances. 

• The role of coral disease as a community structuring force depends on the magnitude, duration

and frequency of reappearance of the disease, and the recovery time of the system. 

• The recovery time depends on the life history strategies of the affected species, including rates of

recruitment and growth.

• The impact from disease is likely to vary depending on the overall condition of the reef,

including the cover and composition of reef building corals, the presence and abundance of

critical indicator species (e.g., Diadema), and the degree of physical, environmental and

anthropogenic stressors.

A. Fates of infected corals

Coral diseases can cause rapid rates of tissue mortality, but rate of tissue loss within a colony is

highly variable depending on the disease, affected species, location and season (Table 6). Diseases may

produce mortality of affected corals over varying periods of time, although diseases more often cause

only partial mortality (Bruckner and Bruckner, 1997 c). While corals have the potential for recovery

once the insult is eliminated, the reduced size of affected colonies may affect growth, reproduction,

resistance to injury and other diseases, and competitive abilities of the surviving polyps (Edmunds,

1991). Colonies affected by disease are vulnerable to reinfection, infection by other diseases, or

subsequent attacks by predators and overgrowth by competitive invertebrates and algae (Kuta and

Richardson, 1996; Bruckner and Bruckner, 1997 a; Antonius and Riegl, 1997; 1998). For instance,

Bruckner and Bruckner (1997 a) reported a recurrence of BBD later in the season or in subsequent years

(1995-1996) in 39 corals (11.4%) identified with BBD in 1992 or 1993.
17

B. Effects on coral populations

Coral diseases, once they invade a reef system, may become a chronic feature of that system

which undergo periodic escalations in abundance and virulence (Bruckner, 1999; Richardson and

Aronson, in press). From an evolutionary standpoint it is not beneficial for a microbial pathogen to

eliminate all of its host species. A coral species may occasionally suffer periods of high mortality from

disease, however survivors are likely to persist by becoming resistant, the pathogen may undergo a

decrease in virulence, or that disease may occur on a wider range of host species or over a wider

distribution. For instance, Dustan (1977) observed an epizootic of white plague in 1975 that was

predicted to result in the disappearance of Mycetophyllia ferox from Carysfort Reef in the Florida Keys. 

This species still occurred on this reef in 1984, and most colonies were not observed with white plague,

suggesting that this species developed a resistence to the pathogen and new colonies recruited onto this

reef to replace those lost to disease.

Table 6. Rates of tissue loss ands extent of mortality from black-band disease.

Affected species linear spread Tissue loss

(observation period)

Total loss/season Location &

Source

M. annularis (n=2)

D. strigosa (n=1)

0.3-6.2 (mm/da y)

2.4-4.0 (mm/da y)

64-746 cm2 (41 days) 1509-4820 cm2 Belize; Rutzler et al.,

1983

D. strigosa (n=12) no data 7 colonies lost >75% live

tissue; 3 lost 50-74%; 2 lost

<25%

USVI; Edmunds,

1991

S. siderea (n=93)

M. cavernosa (n=48)

no data 1810 cm2

 (2 years)

1630 cm2 (2 years) 

Small colonies (mean=239

cm2)died in 1-8 months.

Large colonies of Ss lost 50%

live tissue in 2-3 years; large

colonies of Mc lost 68% of

live tissue. 

Jamaica; Bruckner

and Bruckner, 1997a

M. annularis

D. strigosa

up to 1 cm/day Antonius, 1981

M. annularis

M. faveolata

M. franksi

M. cavernosa,

D. strigosa

D. clivosa

C. natans

S. siderea (n=210)

0.5-8.1mm/day

Variations among

species, reefs and

depths. Slowest

spread among S.

siderea in deep

water and fastest

among M. annularis

in shallow water.

1.3-100 cm2 /day

107-1329 cm2 total 

Mean duration of BBD=

46-220 days.

Mortality rates depended on

species, reef and depth and

also size of coral, length of

BBD and duration of BBD. 

Mean loss (pooled by species)

ranged from 18%-96%.

Puerto Rico;

Bruckner, 1999

M. faveolata (n=9)

D. strigosa (n=51)

4.1 mm/day

2.0 mm/day

Honduras; Griffin,

1998
18

(Dustan, 1987). In contrast, M. faveolata colonies showed few signs of recent tissue loss in 1975, while 

many were infected with white plague in 1985 (Dustan, 1987). More recently, Richardson et al. (1998)

reported an outbreak of white plague in the Florida Keys which initially targeted Dichocoenia stokessi, a

species that was not affected by plague in the 1970s or 1980s. Between 1995-1997, white plague spread

among 17 coral species in the Florida Keys and the rate of tissue loss was much greater than that

observed in earlier years. These observations led Richardson (1998) to conclude that this disease

outbreak involved a more virulent pathogen than that reported by Dustan (1977). The outbreak was one

of the most severe disease events in terms of diversity of species affected, mortality rates, and rapid rate

of spread throughout the reef tract, but was believed to have minimal long-term impacts, as disease

incidence was greatly reduced in these sites in subsequent years, and the pathogen identified as the cause

no longer appeared to induce disease signs (Richardson and Aronson, in press). Another outbreak

(termed plague type III by Richardson) was observed in 1999 on the same reefs; rates of tissue loss

exceeded that reported for earlier outbreaks, and large faviid corals (M. faveolata and C. natans)

appeared to be most susceptible (Richardson and Aronson, in press). 

C. Effects on ecosystem structure and function

When diseases have particularly severe impact on populations of a single species, the effects can

extend over the entire ecosystem. Diseases may exert a major control on biodiversity by eliminating

certain highly susceptible species and losses may reduce the capacity for the ecosystem to sustain

associated species. Until about 1980, more than 95% of the total coral coverage in the reef crest and

shallow fore reef consisted of A. palmata and A. cervicornis, with colonies forming extensive high relief

thickets (Gladfelter et al., 1977). Populations of acroporids were reduced to unprecedented levels

throughout the Caribbean during the 1980s and 1990s (Aronson and Precht, 2001). The combination of

coral mortality, declining herbivory (associated with the Diadema die-off and overfishing of parrotfish

and surgeonfishes), and possibly elevated nutrients have precipitated a phase shift from coral to

macroalgal dominance (Hughes, 1994; Aronson and Precht, 2000). In many locations, A. palmata

colonies suffered near total mortality, but erect skeletons remained in growth position, continuing to

provide high-relief habitat. However, exposed skeletal surfaces were rapidly colonized by invertebrates

and algae and skeletons are being progressively bioeroded, dislodged and removed during storms. The

collapse of acroporid skeletons is associated with the elimination of high relief, three-dimensional

topography. Long-term consequences may include loss of critical habitat and refuge for a wide number

of associated species, reduced rates of reef accretion, and reduced shoreline protection from tropical

storm waves.
19

7. Measures to mitigate disease impacts 

The problem: Resource managers need tools to combat disease epizootics, prevent future outbreaks, and reduce the

time needed for recovery of affected reefs and species

In the past two decades numerous reef mitigation and restoration projects have been undertaken

in response to coral mortality, in attempt to offset these losses. While the majority of these projects have

been undertaken in response to direct human impacts (e.g. ship groundings), limited restoration efforts

have been conducted to rehabilitate areas degraded by coral mining, blast fishing and other human

impacts. A variety of treatments have also been attempted for corals with disease, including application

of antibiotics, removal of the microbial community, shading, and biological controls(Peters, 1997;

Griffin, 1998; Bruckner, 1999; Franklin, 1999; Borneman, 2001). In addition, attempts have also been

undertaken to treat corals with YBD (A.W. Bruckner, unpubl. data) and white plague (S. Miller, et al., in

press) involving application of putty or clay over affected tissue. These approaches have had varying

rates of success, but most attempts have been conducted on a very small scale and often only limited

efforts have been made to determine the long-term benefits. As an alternative to direct treatment of

diseased corals, novel biological restoration approaches are being applied in Florida and other locations. 

These approaches are designed to enhance recruitment of corals, reduce coral mortality, and improve

habitat quality, and include the reintroduction of Diadema antillarum as a tool to reduce macroalgae and

induced settlement of coral larvae (M. Miller, unpubl data). 

In response to an outbreak of BBD in the Florida Keys in the 1980s, Harold Hudson attempted

to treat colonies through aspiration of the BBD using a boat-operated vacuum pump, followed by

application of modeling clay over the affected area to prevent reinfection. Unfortunately, colonies were

not tagged or followed to determine their fates. In 1998, Hudson and Franklin repeated their initial

experiments in response to another outbreak of BBD (Hudson, 2001). An experimental approach to treat

BBD corals was undertaken by Bruckner (1999) in Puerto Rico. The experimental design included 1)

removal of the BBD using a large hypodermic syringe to aspirate the BBD . In these experiments, the

affected area was unmanipulated, covered with modeling clay, or covered with underwater putty; 2)

application of underwater putty directly over the BBD; 3) shading using various grades of sun screen;

and 4) addition of Diadema antillarum to cages containing BBD-infected corals. All treatments were

effective to varying degrees, with the highest success (>95%) achieved with the use of underwater putty,

and very low success when removal was combined with modeling clay (Bruckner and Bruckner, 1998d).

Putty proved to be a highly efficacious treatment which prevented further destruction of century-old

colonies, and may be most suitable when applied on a small scale for those colonies most important to
20

the persistence of the reef (e.g., the largest colonies of slow-growing massive species). However, it may

be impractical to treat a large number of corals due to the time required to manipulate infections and the

expense associated. Because BBD is spread by water motion, care must also be taken to remove the

bands without liberating filaments into the water column, which could result in additional infections

downstream.. There are a few other limitations associated with treatments discussed for BBD: 1)

aspiration of BBD followed by application of clay may be unsuccessful because any remaining

Phormidium filaments are capable of emerging from within clay; 2) shading may cause coral bleaching;

3) Diadema may injure coral tissue when grazing pressure exceeds available algal resources.

Hayes and Goreau (1998) recommended rapid isolation and removal of diseased colonies to

provide protection for other reef constituents against the spread of disease. However, this approach is

likely to have minimal benefits, as the removal of an infected host may actually promote dispersal and

spread of the pathogen, and it may result in considerable habitat damage. Furthermore, low background

levels of disease may be a normal occurrence on most reefs that require minimal management

interventions, while a disease epizootic is of much greater concern and yet it would be very impractical to

remove all corals affected during a disease epizootic. Another proposed strategy, that may have severe

long-term consequences, involves the application of antibiotics. Broad application of antibiotics are not

recommended, as they may affect beneficial microbes and can lead to the proliferation of antibioticresistant pathogens. However, some researchers have proposed adding antibiotics to putty or clay, to

restrict treatment to affected areas and contain the antibiotic, which may be much more plausible.

Proposed strategies to address management needs for coral diseases

1. Early warning systems

Remote sensing of coral reefs, using high resolution satellite sensors, airborne LIDAR and

hyperspectral coverage, and acoustic mapping methods are important tools to characterize ecosystem

types and features, classify human use patterns, and determine sea surface temperature, water mass

movements, light exposure, and other physical properties. Satellite remote sensing measurements (ocean

color, surface winds, and insolation data) are being used in NOAA’s Coral Reef Watch Program to

conduct thermal bleaching surveillance of coral reefs world-wide. In this program, oceanographic data

are integrated with a GIS spatial database to produce high resolution “HotSpot” (bleaching anomaly)
3NOAA/NESDIS Coral Reef Watch incorporates the Coral Reef Early Warning System (CREWS) and OAR/AOML

international coral reef information system. This information is available through the Coral Health and Monitoring

Program (CHAM P) Web P age: http://www.coral.noaa.gov.

21

charts available on the world wide web3. Also, a series of moored buoys are being deployed as part of a

Coral Reef Early Warning System (CREWS) in the NWHI, U.S. Pacific, Florida, the Bahamas and other

locations. These permanent oceanographic stations provide detailed in situ measurements of a variety of

water quality parameters including water and air temperature, light (PAR and UV), nutrients, wind speed

and direction, and water currents. Through the Coral Health and Monitoring Program (CHAMP) corallist server, NOAA regularly announces sites that are affected by high sea water temperatures as a

warning for potential bleaching. Researchers are then able to verify the onset of bleaching, and

subsequently monitor impacts associated with the event. For instance, these data demonstrated accurate

capabilities for detection of El Niño-induced coral reef bleaching in 1998. Some coral diseases become

more prevalent during warm-water periods, and “HotSpot” data may also prove useful in understanding

relationships between coral bleaching and disease. It is important to link oceanographic data with rapid

assessments for disease. Real-time information on environmental stressors could provide valuable

insight into identifying indicators of reef health, and factors that trigger disease outbreaks.

2. The spatial distribution and temporal variations of coral disease outbreaks

Specific monitoring programs need to be developed to provide information on disease occurrence

and progression at a variety of temporal and spatial scales using standardized techniques suited to answer

specific questions on coral diseases. Because diseased corals often occur at a low frequency and in a

clumped distribution, surveys must encompass large areas to quantify the distribution and abundance of

diseased colonies (Edmunds, 1991). Surveys must also be conducted relatively frequently to identify

temporal variability, quantify synergistic impacts, and distinguish mortality from disease from mortality

caused by other factors. 

An effective program should include a three-tiered approach. First, rapid assessments conducted

on a regional scale can elucidate large-scale processes such as the transmission of regional-scale waterborne pathogens, and serve as an early warning system to identify and track disease outbreaks before

irreparable harm occurs. Targeted monitoring can provide information on a particular disease, and

intensive seasonal or weekly monitoring of specific reefs can help managers understand the effect of a

particular disease at a local scale, or the role of a localized stressor on disease processes and impacts. 

Monitoring of individual colonies affected by disease is also necessary to document patterns of spread,

the rate of spread and amount of mortality sustained from individual infections, impacts of diseases at
22

colony or population levels, and relationships between disease occurrence and other natural or

anthropogenic impacts. 

A variety of approaches have been used to identify the prevalence (number of affected corals

divided by the number of corals examined) and incidence (number of new colonies with disease

occurring in a population over a given time divided by the number of unaffected individuals at the

beginning of the time period) of coral diseases, including quantitative, semi-quantitative and qualitative

surveys (Table 7; Appendix I). Many monitoring programs rely on repeated sampling of permanently

marked transects, quadrats, or radial study sites. Detailed monitoring of particular reefs, through the

establishment of permanent sites, can provide information on disease incidence. In addition, long-term

monitoring of individual tagged colonies affected by microbial pathogens can provide detailed

information on the duration of infections, frequency of reinfection, and effect at the species level. 

Monitoring programs that involve the reexamination of permanent sites may be impractical for

sampling more than a few sites or reefs, and may underestimate or overestimate the prevalence or

potential impacts. Because diseases often occur at a low frequency or they exhibit a clumped

distribution, a large number of transects may be required within each reef to accurately estimate disease

prevalence. To obtain a more realistic measure of disease prevalence overall at a larger (country-wide or

regional) scale, and to determine factors responsible for the increase and spread of diseases, a repeated

measures approach consisting of multiple random belt transects positioned throughout each reef

environment is necessary.

Specifically, a monitoring program implemented for coral diseases at the community level is needed to

obtain information on: 

• The type of disease, coral species affected, and variability among species.

• The prevalence and incidence of diseases, the duration of a disease outbreak or bleaching event,

and the consequences to affected species.

• Physical parameters (depth, water clarity, temperature etc.), biological factors (predators, algal

abundance, etc.), and environmental stressors and anthropogenic impacts associated with the

outbreak.

• Local, regional, and global distribution of diseases and temporal and spatial variations.
23

Table 7. Monitoring and assessment techniques used for coral diseases. 

Monitoring

Approach

Cond ition exam ined. Description of technique Author

Timed

swims

All syndromes. Diver swims for 30 minutes along a single depth gradient and examines all

corals in a band approximately 2 m wide recording the type of disease, species an d number of

affected corals. Disease occurrence is categorized as rare (1-3 cases), moderate (4-12 cas es),

frequent (13-25 cases), abundant (26-50 cases), epidemic (51-100 cases) or catastrophic

(greater than 100 cases).

Antonius, 1995a

Radial sites Prevalence and inc idence of BBD; Total number of infected and uninfected colonies of each

species present are recorded within a circular area (10 m radius; 314 m2

).

 Edmunds, 1991; 

Kuta and Richardson,

1996; Bruckner et al.,

1997a 

Radial belt

transect 

 All diseases on stony corals and gorgonians. Total number of affected and un affected

colonies of each species present are recorded within the outer 8- to 10-m of an arc radius

(circular area, 10 m radius; 314 m2).

Santavy et al., 2001

Linear

transects

A. Changes in composition, size and cover. Twenty 25m transects on Carysfort Reef from 

0.3 to 21m depth. Permanent transects were extended parallel to each other and subdivide an

area approximately 25 m X 300 m. Mean colony size (length under the transect line) and

distance between colonies were recorded; colonies were inspected for signs of mortality

(disease, physically damaged areas, sediment covered tissue or other blemish).

B. Condition of stony corals. Minimum of ten 10m transects per reef/depth; surveys at 3m

and 10m depth; record species, size, percent recent and old mortality of all colonies that touch

the transect line; examine whole colony for diseases or other source of mortality.

A. Dustan, 1985

B. AGRRA, 1998

Belt

transects

A. Sea fan disease. One or two 4m X 12.5-50m transects per country. 

B: All diseases; corals and gorgonians. Ten 10 X 2m belt transects (level 1) and three 20 m

X 2 m belt transects per depth; minimum 9 transects at each site (level 2).

C. Reef condition. Three 20m X 5m tra nsects per reef; divers note presenc e and proposed

type of disease and affected species, but do not collect quantitative information.

A. Nagelkerken et al.,

1997; 

B. CARICOMP

(Appendix I)

C. Reef Check

Quadrats A. BBD in Gorgonians. Prevalence: three 100 X 250m quadrats; incidence: one 10 X 10m

quadrat; on e reef

B. Sources of mortality. Photostations 2 X 2.25 m; 2 per reef; 2 reefs to identify sources and

amount of morta lity or time; complemented with permanent chain transects ext ended over

25m to measure changes in percent coral cover, diversity, and colony size. 

C. Coral reef monitoring. 160 stations, each 2m X 22m; sampled 40 sites in the FKNMS. 15-

minute survey of each quadrat to complete a species inventory, identify species that are

affected with bleaching or disease, and record the type of disease. No data collected on

disease prevalence. Also run video transects. Sites reexamined once each year from 1996-

2000.

A. Feingold, 1988; 

B. Porter and Meier,

1992

C. Jaap et al., 2000

3. Relationships with environmental factors, anthropogenic stressers and natural disturbances

If there is a link between anthropogenic pollutants, nutrients, and sedimentation and the

prevalence of coral diseases, disease occurrence is unlikely to be randomly distributed at regional scales. 

An understanding of the global epizootiology of diseases constitutes a first step in examining

relationships between human impacts and the occurrence of coral diseases. A comprehensive database

needs to be developed linking all accurate field reports by trained observers as well as observations and

photographs from amateur observers to understand the impacts of coral reef diseases on a global scale
4

http://www.unep -wcmc.org /marine/cor aldis/home .htm

24

(Goreau et al., 1998). The Global Coral Disease Database4, developed by NMFS in conjunction with

UNEPs World Conservation Monitoring Centre (WCMC) provides a first attempt at analyzing the global

distribution of diseases (Green and Bruckner, 2000). This web-accessible database provides information

on the reported types of disease, species affected, and global distribution of each disease. Disease

occurrence can be mapped by particular disease, location, or year. Currently, the database contains all

published records identified through 2000, as well as volunteer disease reports; a form is available for

reporting disease data electronically. The database is being expanded to include new regional monitoring

data from AGRRA, CARICOMP and other sources, with a separate category for volunteer diver reports

of disease (non-experts). Furthermore, additional layers will be added to the GIS database that map

environmental and anthropogenic parameters. This information will facilitate interpretation of disease

epizootics and causative factors involved in the development of these outbreaks. 

In addition, targeted research that combines both laboratory and field methods is needed to

understand the influence of various stressors on coral diseases, bleaching and mortality. These efforts

should focus on establishing cause-effect thresholds of anthropogenic pollutants and environmental

stressors, and capabilities for providing early warnings of disease outbreaks. For example this could

include studies on:

• Mechanisms and factors that increase/decrease host susceptibility to disease. 

• Cellular, mechanical, chemical and behavioral mechanisms that impart host resistence and host

defense to diseases, and the ability of a host to counteract disease agents. 

• Genetic adaptations and resistence of specific clones of coral colonies. 

• Identification of biomarkers of exposure or effect of stress to corals resulting from anthropogenic

impacts or environmental perturbations. 

4. Standardized nomenclature to describe, identify and differentiate diseases

A method to categorize disease terminology and standardize the list of recognized diseases is

essential in attempting to assess the global implications of disease. Classifying the various visual

categories of recent mortality as well as deviations from normal coloration or morphology is necessary to

correlate damage with causes (Santavy and Peters, 1997). Field observations must be combined with

techniques from biochemistry, histopathology, and microbiology to determine whether diseases are

microbial or abiotic in nature, to identify and differentiate disease-causing microorganisms, megafauna
5

http://ourworld.comp userve.com /homepa ges/mccarty_and_p eters/corald is.htm

25

(corallivores) and environmental stressors associated with each condition, and to develop molecular tools

to validate field identification of diseases that are difficult to visually identify (e.g., aspergillosis). 

As a first step, the list of all known and presumed coral diseases (Table 1 and 2) should be

evaluated for its validity. Accepted terminology should reflect the first name assigned to a condition, and

terminology to describe presumed “new diseases” should be discarded if the condition was previously

described. For instance, the condition “rapid wasting syndrome” described in 1998 was called

“parrotfish white spot biting” in literature from the 1980s. Separate terminology should also be used for

syndromes that visually differ to avoid confusion. This includes “yellow-band disease” which was first

described in acroporids and other species in the Arabian Gulf, and later used to describe an unrelated

condition in faviid corals (primarily M. annularis complex) from the western Atlantic (Cervino et al.,

2001). Santavy and Peters (2000) recommended the use of yellow-blotch disease for the condition

affecting M.faveolata and M. annularis, thereby differentiating it from the yellow-band disease affecting

Pacific corals.

Disease nomenclature may evolve from descriptive terminology to etiological and

pathognomonic characterizations (e.g., aspergillosis) (Hayes and Goreau, 1998). Hayes and Goreau

(1998) suggest that conditions where no microbial pathogens are identified may be better classified as

stress responses, while pathogenic diseases should be renamed to indicate the specific organisms

implicated as the causative agent. However, several contributing microbes may be required to produce a

disease sign, such as that observed in BBD, making a single name (e.g., cyanobacteriosis) impractical or

incorrect. In other cases, the proposed pathogen may not be the initial cause, but a secondary invader. 

Conclusive demonstration of the causative agent (and verification according to Koch’s postulate) has

proven difficult, and positive identification of the cause of some diseases may not be possible in the

immediate future. Because diseases manifest on corals in a limited number ways, corals that exhibit

specific disease signs in the field may be affected by a variety of pathogens that differ spatially or

temporally (e.g., the pathogen for plague may differ depending on the location, affected species, or other

factors). 

There are several sources of photographs and descriptions of coral diseases that can assist in

developing a list of recognized coral diseases and descriptions to allow field identification of these

diseases. These include 1) a coral diseases web site by McCarty and Peters5 ; 2) underwater coral disease

and predator identification cards by Bruckner and Bruckner designed to help differentiate signs of

disease from predation (NOAA, 1999); and 3) a recent chapter “Coral health and mortality: recognizing
6

http://www.coral.noaa.gov/

26

signs of disease and predation” in Humann and Deloach, Reef Coral Identification, Florida, Caribbean,

Bahamas 2nd edition (Bruckner, 2001), which contains extensive descriptions and photographs of

diseases, signs of predation, and coral overgrowth. A coral disease identification CD-ROM is being

developed by NMFS and UNEPs-WCMC for distribution to dive shops throughout the Caribbean to

complement volunteer diver disease identification programs. One additional source of information under

development is a comprehensive coral disease website within the CHAMP database 6 designed to provide

help in disease identification and research approaches for laymen, scientists, managers, and disease

specialists. This will contain an identification key for diseases, high resolution photographs showing

diseased corals, tissue sections, and electron micrographs, a Frequently Asked Questions (FAQ) list, a

glossary, contact information for coral disease researchers, a list of publications on disease, and PDF

files of relevant publications.

5. Factors that facilitate the occurrence, spread and transmission of pathogens

A multidisciplinary effort is necessary to conduct controlled experiments that evaluate possible

sources of pathogens, identify mechanisms of dispersal and spread, and develop strategies to reduce the

potential for introduction and spread of pathogenic organisms. This includes:

• Evaluation of the role of water circulation as a vector for dispersal of pathogenic

microorganisms. 

• Examination of microorganisms transported in African dust, through species introductions, from

discharge of ballast water, and other possible external sources of pathogens. 

• Examination of microbial populations found in sediment adjacent to corals and microbiota

associated with coral mucus. 

• Evaluation of other possible sources of pathogens, including algal and cyanobacterial mats that

occur in benthic habitats outside of disease associations.

 

• Identification of conditions and factors that promote the proliferation of pathogenic

microorganisms and/or affect their virulence.

6. Effects on population dynamics, community structure and ecosystem function

Long-term monitoring of individual colonies and species affected by disease should be

conducted to determine their fates, factors that may increase or decrease the amount of mortality and

their potential for recovery or recolonization, and the effects of coral mortality on associated species and

coral reef community structure and function. Relevant studies include:
27

• Monitoring of individual colonies to determine the rate of tissue loss, extent of mortality, effect

on physiological processes such as growth and reproduction (for corals that experience partial

mortality), differences among and within diseases, coral species, seasons, depths and locations,

and synergistic effects of other stressors.

• Evaluation of the fates of coral skeleton exposed by diseases, including the potential for corals to

regrow over the affected areas, extent of colonization by algae and invertebrates (especially

organisms that bioerode coral skeletons), and the extent of coral recruitment.

• Examination of relationships among reef-building coral species and associated species and in the

composition, structure and function of reef communities, and the role of diseases in structuring

communities and influencing relationships among predators, competitors and other reefassociated organisms. 

7. Measures to mitigate disease impacts 

The ability for resource managers to effectively address coral disease epizootics and mitigate

their impacts relies on an understanding of the causes, species affected, spatial and temporal prevalence

and incidence, and synergistic effects of climate change, human impacts and other stressors (e.g.,

hurricanes). Research should focus on the development of techniques to prevent the occurrence of

diseases, cure diseases, and minimize the effects of disease. This includes:

• Strategies to reduce relevant stressors that are correlated with the occurrence, virulence or spread

of diseases. 

• Novel biological, ecological and physical techniques to improve habitat quality and water

quality, and potential reintroductions of ecologically important species that were formerly

abundant but have declined due to human pressures or other disturbances, including predators,

competitors, or other organisms that may help counteract the disease-causing agent. 

• Treatments for corals with disease, including efforts to reduce host contact with pathogens and

increase host defense and resilience. 

• Restoration approaches to enhance coral recruitment and introduce disease-resistant clones of

species impacted by disease that are unlikely to recover naturally in the short term. 

All efforts to mitigate diseases should involve hypothesis-driven experiments to determine the

effectiveness of these approaches. 

CONCLUSION

Most managers and policy makers are aware of the continued, rapid degradation of coral reefs,

and they recognize that many of the stressors responsible for these changes are increasing in severity.

Coral diseases are receiving increased attention by scientists and the media as an important source of

coral mortality, but several factors hinder the development and implementation of strategies necessary for
28

rapid response to diseases, and management of disease-related impacts. This includes difficulties in

obtaining funding for monitoring and targeted research needed to address many unanswered questions

regarding diseases. It is also apparent that there is a lack of coordination among research scientists

which must be overcome. Research on coral diseases requires an approach that combines ecological

monitoring with biochemistry, molecular biology, histology, toxicology, physical oceanography, ecology,

taxonomy and other laboratory and field methods. An interdisciplinary approach is necessary to

identify, differentiate and characterize coral diseases and their consequences, and understand

relationships among diseases and other biotic and abiotic factors. To achieve an understanding of

diseases at local to global scales requires considerable investment of time and effort to survey large areas

of reef, and to conduct these surveys at frequencies that are sufficient to document the duration of the

condition, seasonal patterns, or chronic effects. These studies must be combined with research to

elucidate relationships with environmental and anthropogenic stressors, which may help explain

differences observed at regional to local scales, and to identify approaches to mitigate disease impacts.

The policy and decision-making processes necessary for effective conservation of reef

ecosystems, including the development of appropriate actions to manage coral diseases, are influenced by

equally complex socioeconomic and political systems. There is a limited awareness and recognition of

the potential global implications of disease by policy makers and the public who may have the tendency

to overlook diseases, partly because they are not charismatic. Important decisions that must be addressed,

such as the regulation of coastal development or implementation of strategies to control land-based runoff must occur over large spatial scales and be in effect for long time periods. The science in support of

these decisions is often conducted on much smaller spatial and temporal scales. Also, it may involve

highly specialized research with results that are difficult to apply directly to policy decisions, or the

science may be completely lacking. Given limitations of existing funding, coral disease research should

be targeted towards efforts with the greatest management benefits that can be applied over large spatial

scales, and research must also be relevant to understanding diseases and their impacts, and mitigating

their effects.
29

ACKNOWLEDGMENTS

The National Ocean Service (NOS) convened a workshop in Charleston, South Carolina on 22-25

January 2002 as part of the Coral Disease and Health Consortium’s (CDHC) efforts to develop a

National Research Plan to improve our understanding of coral diseases. This paper was developed to

provide an overview of what is known about diseases and to identify information needs of coral reef

managers that could be provided through rapid ecological assessments, long-term monitoring, and

targeted research. I am grateful to Dr. Cheryl Woodley, the head of CDHC, for the opportunity to

present this information to the workshop participants. Comments on an early draft were provided by Dr.

Tom Hourigan and Robin Bruckner. The final preparation of this report was greatly improved from

reviews by Dr. Esther Peters, Dr. Deborah Santavy and Eric Borneman. Dr. Ernesto Weil and Dr. Debbie

Santavy provided information on the monitoring protocols described in Appendix I, and Dr. Brian Keller

and Billy Causey provided information on the management and science objectives for the FKNMS.

Finally, I want to recognize the support of the National Marine Fisheries Service Office of Habitat

Conservation and the Coral Reef Program in encouraging the preparation of this document, in

supporting its publication, and in its distribution to those working on coral reef issues. The opinions and

views expressed in this document are those of the author and do not necessarily reflect those of the

National Marine Fisheries Service, National Oceanic and Atmospheric Administration or the U.S.

government.
30

APPENDIX I: Monitoring and Assessment Approaches

I. Atlantic and Gulf Rapid Reef Assessment Protocol

The following description represents the benthic survey method for corals. The assessment technique

involves 10m transects placed along depth gradients at haphazard, non-overlapping intervals. The

condition of corals that touch the transect are assessed. The full protocol can be obtained at: 

http://coral.aoml.noaa.gov/agra/method.htm

The AGRRA method is focused on assessing the condition of the principal scleractinian and hydrozoan

corals that contribute most to the three-dimensional structure and complexity of reefs. The vitality of

these corals responsible for the construction and maintenance of reef framework is important for the

long-term persistence of a coral reef. The AGRRA method assesses overall coral cover, and for each

coral, assesses the amount of partial coral mortality (both recent and old), size and height, incidence of

bleaching/diseases, causes of mortality, and number of damselfish.

AGRRA makes a further distinction of mortality into partial mortality that includes both Arecently@ dead

and Aold@ dead. ARecently dead" is defined as any non-living parts of the coral in which the corallite

structures are white and either still intact or covered over by a thin layer of filamentous algae or mud. In

contrast, "old dead" is defined as any non-living parts of the coral in which the corallite structures are

either gone or covered over by organisms that are not easily removed (e.g., certain algae and

invertebrates), even if the outline of the dead corallites is still visible below (e.g., certain

zooxanthella-containing boring sponges that overgrow their substrates).

Causes of partial mortality include, but are not limited to grazing (e.g., parrotfish bites), extended

bleaching, sedimentation, algal overgrowth, disease (e.g., black band), and corallivores. To regenerate

injured tissue, corals must reallocate energy that would otherwise be used for energy storage, growth or

reproduction. It is fairly common for corals to experience partial mortality and to regenerate these areas if

the lesions are not too large, relative to their remaining live tissues. Most partial mortality is small in

size, but above certain sizes, which vary with the species and the kind of injury that has been received,

dead skeletal areas tend to become overgrown or eroded by algae or other bioeroding organisms. In cases

of large lesions, corals often will put energy into marginal growth instead of regenerating new tissue over

the dead area.

By quantifying the amount of recent mortality, you sum the extent of any damage and obtain information

on whether the corals are likely to recover. Several studies have shown that the extent and amount of

partial mortality is related to differences in size, morphology, species identity, and differences in the

spatial and temporal distribution of predators. Normally, small corals often have either no injuries or total

mortality, while larger corals are likely to survive partial mortality. The AGRRA data can be used to

calculate size frequency distributions as well as mortality patterns related to size and, when sample sizes

are large enough, species identity. This allows the added benefit of being able to examine coral

size-frequency statistics to assess a population structure and interpret levels of mortality. Although there

are studies showing the importance of size-frequency distributions in population dynamics, additional

research is required to determine Anormal@ size-frequency distributions for major reef-building species in

various habitats.

Areas of recent mortality and adjacent coral tissues should be examined closely to determine if calices

are disrupted or damaged (fish bites), if corallivores are present (e.g. gastropods or polychaetes), if

polipary and coenostial structures are abnormally large or form aberrant masses (hyperplasm or
31

neoplasm), or if other disease conditions exist. Diseases are recorded based on color, including black

(black band), white (white band or other white-type diseases in acroporids; white plague in massive

corals), yellow (yellow blotch) or red (red band). White areas must be examined closely to distinguish

areas without living tissue (e.g. exposed skeleton caused by disease or predation) from bleached tissue.

Dark-spot disease also has a mottled appearance, however it is manifested as irregular patches that are

darker than the normal pigmentation and these areas may be slightly depressed. Predation can often be

differentiated from disease (and bleaching) by examining tissues at the interface of white, exposed

skeleton; diseased tissue will appear irregular and may be sloughing off the skeleton. Elevated

Achimneys@ on Acropora spp. and Aridge mortality@ on brain corals are induced by repeated three spot

damselfish (Stegastes planifrons) bites.

1.At each SITE, haphazardly lay the 10-m transect line just above the reef surface in a direction that is

parallel to the long axis of the reef. Make sure the line is taut.

 

Note: Be sure to avoid or cross any other transects that are being set by your companions, and stay away

from the edges of the reef. Also try to avoid areas with abrupt changes in slope, deep grooves, large

patches of sand or unconsolidated coral rubble. You want to place the transect in areas where corals are

likely to grow. Unusual reef features should only be included to the extent appropriate to their relative

abundance at the site. 

 2. Approximate live coral cover by swimming along the transect line with your 1 m measuring device

and roughly estimating how many meters of the line is underlain by living coral (to the nearest 10 cm).

Be sure to include all live stony corals below the line, regardless of size or species density (but remember

do not include dead skeleton). Record this total. If the reefs are too small for you to avoid sandy patches,

record how much of the transect line crosses sand, to allow a later calculation of the number of coral

heads encountered/m of reef surface. 

3. Swim towards the other end of the transect and stop at the first coral head, cluster, or thicket (or a

portion) of the appropriate species that is located directly beneath the transect line, is at least 10 cm wide,

and which is in original growth position. For a colony that has fallen or been knocked over, only assess it

if it has become reattached to the substratum or is too large to move. If the colony is loose and rolling

around, then skip it. For each coral surveyed, record each of the following:

 

A. Name (genus and species) 

B. Record the water depth at the top of the corals at the beginning and end of each transect. In cases

where bottom topography is very irregular, or the size of the individual corals is very variable, record the

water depth at the top of each coral beneath the transect line at any major change in depth (>1m). 

C. Identify the colony=s boundaries based on connective or common skeleton, connected live tissue,

polyp size, and polyp color. Using a measuring device, measure to the nearest cm, its maximum projected

diameter (live + dead areas) in plan view and maximum height (live + dead areas) from the base of the

colony= substratum, not the reef=s substratum or ocean floor. The diameter should be measured

perpendicular to the axis of growth. The height should be measured parallel to the axis of growth. Plan

view is assessed from an angle that is parallel to the axis of growth. 

Note 1: Some surveyors may want to measure all sizes of corals (even <10 cm max. diameter) on reefs on

which large colonies are scarce. They are encouraged to do so, but only data based on corals greater than
32

10 cm will be directly comparable to other AGRRA results). In previous years we suggested measuring

corals >25 cm, but based on consensual agreement we have changed it to >10cm. 

D. Estimate the percent (%) of the coral that is "recently dead" and the % of the coral that is

"Long dead" as viewed from above in "plan" or "map" view. Plan view is assessed from an angle that is

parallel to the axis of growth (be prepared to tilt your head to find the axis of growth and establish the

proper plan view). 

 "Recently dead" is defined as any non-living parts of the coral in which the corallite structures are

white and either still intact or covered over by a layer of algae or fine mud. For recent mortality, there are

several Astages@ of recent

 Very recent = white intact skeleton is still visible (dead w/in 1 month or less)

 Recent = corallite may be covered by thin turf algae or sediment (up to 6 months)

 Older recent = corallite structure may be slightly eroded or covered but can still identify to genera 

(< 1-2 yrs), unless covered by clionid sponge

E. Combine all of these recent mortality categories into RECENT. In some cases circular or oblong

lesions or excavations caused by fish biting may result in destruction of the corallite. If fish bites are

identifiable and constitute part of the mortality, consider it as recent mortality. 

Note 1: "Long dead" is defined as any non-living parts of the coral in which the corallite structures are

either gone or covered over by organisms that are not easily removed (certain algae and invertebrates). If

it is entirely Along dead@, indicate this on your data sheet as 100% Along dead@, as long as you can

identify it to generic level based on morphology (e.g., Acropora palmata) or skeleton (e.g., Diploria sp.). 

Note 2: In some cases, a coral may be partially or completely overgrown by the brown encrusting sponge,

Cliona sp. At a quick glance, it may look like live coral tissue, but if you look closely you may observe

the in/ex- current holes of the sponge and sponge tissue and will not observe live coral polyps. If you can

see the coral skeletal structure underneath and are able to identify it to genus (e.g., Diploria and

Montastraea), this should be considered old mortality and you should note Cliona overgrowth in

comments.

Note 3: If a coral like columnar M. annularis or Dendrogyra has been knocked over, has either

reattached to the substrate or is too large to move, has started to regrow towards the water=s surface, it

now has a different diameter and height because of its new growth direction. You should measure

diameter, height, and mortality in the correct plan view along the new axis of growth. Only measure the

recently Alive@ part of the M. annularis when estimating mortality and not the old Abase@ because this will

skew old mortality. Quickly scan over the surviving portions of the ENTIRE coral colony and note if

there are any DISEASES and/or BLEACHED tissues present. Characterize any DISEASES by the

following color categories: BB = Black band

 WB = White band

 WS = White spots, patches or pox

 WP = White plague

 YB = Yellow blotch (sometimes called yellow band)

 RB = Red band

 UK = Unknown
33

II. CORAL-OCTOCORAL DISEASE SURVEY - PROTOCOL LEVEL-2 CARICOMP. Modified

by E.Weil June of 2000.

OBJECTIVES:

To assess the occurrence (incidence at population and community levels) and local/geographic

distribution of coral and octocoral diseases across the wider Caribbean region.

More specifically : 1- To quantify relative frequencies of infected colonies in each coral species affected

within and across localities. 2- To quantify relative frequencies of the different diseases within and

across species and within and across localities. 3- To determine if there is a correlation between

frequencies of diseased corals with depth, and distance to anthropogenic affected areas.

LEVEL- 1 - PROTOCOL:

Protocol will work with many different sampling methods (quadrats, chain transects, belt

transects, etc.). This is to be carried out at the two reef sites of the CARICOMP reef monitoring using the

chain. The survey is organized in a hierarchical way that will facilitate the decision-making process. A

set of bilingual-underwater-laminated cards (Bruckner & Bruckner & Weil) was selected to be

distributed amongst all site directors. These ID cards are to be used as a the ONLY guide to identify the

different diseases and other causes of coral mortality. This will serve as a tool to standardize the

identification of the different diseases and causes of mortality. There are ten, 10 m long chain sections

per locality. Survey should be conducted over a belt transect of two meters wide (one meter on each side

of the chain) by ten meter long (20 m5), for a total of 200 m5 per locality at one depth interval. All coral

and octocoral colonies within this area should be checked and counted. The sample unit is one colony

(ramet). Each coral colony should be identified to species (or genus at least) and/or to either one of the

five colony form descriptors specified in the CARICOMP manual (branching, crustose, massive, foliose

or milleporid). Octocorals should be identified at least at the genera level, or using the four cathegories

(rod, fan, feather, whip) in the manual. 

The first discrimination-category for each colony is whether it is healthy or unhealthy. Healthy

colonies are those without signs of disease, recent injury and/or bleaching. Unhealthy colonies are those

with any signs of disease, recent, open injuries and/or bleaching. A non-healthy colony will then be put

into one of three categories, bleached, injured or diseased. If a colony has a disease and any of the other

two signs (bleaching, injuries) it will be included in the disease category. Notes about the other signs

should be recorded. Bleaching should be verified by looking for the presence of live tissue (but

decolored) and at the pattern of bleaching (usually not a band-like pattern like most “white-type@

diseases; e.g., pale, blotchy or white). Injured colonies include those with damage from predation

(often with skeletal damage), anchors or other physical damage, and overgrowth. If you can identify the

type of damage (small lesions like individual bite marks or large excavations such a anchor damage),

please do so. If the colony is being overgrown by other organisms (algae, zoanthid, sponge, hydroid,

tunicates, etc.) it is important to note which organism (s) are overgrowing it. Colonies with old dead

areas covered with algae but with healthy looking tissues fall into the healthy category. 

A diseased colony will then be carefully observed to identify the disease that is affecting it.

Observations should be compared with the information in the ID-cards to put the colony within any of the

following 9 categories (see below and the flow diagram): 
34

1- Black-Band Disease (BBD) Multispecific

2- White-Band Disease (WBD) Types I and II (only in acroporids for the moment)

3- White Plague-II (WP-II) Multispecific

4- Yellow-Blotch Disease (YBD) Only described in species of Montastraea but also reported in

other favid species.

5- Dark Spots Disease I (DS-I) Small, dark areas with no apparent tissue mortality. Common in

Siderastrea spp.

6- Dark Spots Disease II (DS-II) Large dark areas, larger than the DSD-I; common in M.

annularis and S. intersepta.

7- Red Band Disease (RBD) Careful here since BBD can be seen as red bands too. RBD has

been reported for Gorgonia spp and Agaricids in the Caribbean. 

8- Aspergillosis (ASP) Gorgonia ventalina, G. flabellum, P. americana; other

octocorals (Plexaura flexuosa).

9- White POX (WPX) Round or irregular white areas on surface of Acroporids.

9- Other - this category includes all other Aunconfirmed-pathogenproduced diseases (tumors, hyperplasia, and all the blotches).

COLONY

 |

Identify colony to species or any of the other categories,

(branching, massive, foliose, etc).

|

-------------------------------------------

| |

HEALTHY UNHEALTHY

 |

 ------------------------------------------------------------

 | | |

BLEACHING DISEASED INJURED

Check for presence | (Damaged by :

 of tissue and pattern | Predation, anchors

 of bleaching) | overgrowth, etc)

|

| 

IDENTIFY DISEASE

|

 ----------------------------------------------------------------------------

 | | | | | | | | |

BBD WBD WP-II YBD DS-I DS-II RBD ASP OTHER
35

LEVEL 2 PROTOCOL - CORAL DISEASES .

The purpose of this activity is to assess the incidence of diseases in each coral and octocoral

species at different depth intervals (habitats) and in at least two different reef sites per locality. The

diseases will be identified following the protocol level-1 described above. The field experimental design

is as follows :

1- At least two separated (more than 5 km) reef sites should be selected at each geographic locality

(CARICOMP chapter), and preferably, one near and one far from anthropogenic-impacted areas. A

preliminary qualitative, visual assessment of current levels of disease incidence and depth distribution

within the two different reef localities should be done to determine if coral diseases are common or rare.

2- A quantitative assessment will follow using a modified protocol from the standard CARICOMP coral

survey. Three depth intervals would be selected in those reefs with a depth profile to at least 45 feet deep.

The depth intervals are: 0-15 feet; 16-35 feet and 35-50 feet, so major habitats would be surveyed

(shallow, branching Acropora zone and boulder-crustose platform zone; intermediate depth Montastraea

zone - massive, boulders and platy spp.; and the deeper more diverse zone - foliose, massive and platy

spp). Re-bars or other permanent means of marking the transect position should be hammered into the

substrate for future monitoring. 

In each depth interval, at least three 20 meter long x 2 m (40 m5) wide band-transects should be surveyed

(a minimum of 9 transects/reef, better if 12 transects per reef are surveyed). Two sets of 6 band-transect

each should be separated at least 100 m. In each depth interval a set of two band-transects could be done

using a 50 m long, plastic tape. Once the tape is positioned, two 20 x 2 m bands separated by a 10 m

interval will be surveyed (from 0 to 20 m and 30 to 50 m). A one m long pvc section, marked in cm (100

cm) will be moved along each side of the transect line and every colony of coral and of Gorgonia spp.

will be surveyed using the protocol level 1 described above. 

Once a colony is found to have a disease, two diameters (maximum and minimum) will be measured with

the pvc stick to estimate surface area. ONLY diseased colonies (corals and Gorgonia spp) will be

measured, 

Separation between the consecutive band transects (at same depth interval) should be at least 10 m. If the

reef areas do not have a depth profile or slope, or are such that only two depth intervals can be selected,

the minimum of 12 band-transects should be then spatially distributed within the area. All coral colonies

should be recorded to species (or genus at least) level. 

Confusion of what an individual colony or ramet is will probably arise when branching, columnar or

massive species that have suffered fission (fragmentation and/or partial mortality) are encountered. For

the purposes of this protocol, a ramet is any colony that is spatially separated from any other colonies of

the same species. On some occasions however, it is clear for some fragmented colonies, that in the near

past, there was a physiological and physical connection between two or more ramets (i.e. in massive

colonies suffering partial mortality or broken branches nearby the mother ramet of ramose species). In

these situations, instead of counting 2000 small fragments (i.e. P. porites or M. mirabilis) one should use

common sense and spatially delimit the spread of the individual genet (in the many ramets) and count it

as a single ramet (genet). 

The study is aimed at comparing the incidence of coral diseases between different reefs within a given

location (Cuba, Panama, Venezuela, etc.) and across locations in the wider Caribbean. It is fundamental

to the proposed experimental design to insure the sampling of large reef areas, in order to estimate
36

current levels of disease incidence at a suitable spatial scale. Time window to conduct the surveys is

between July and October. Frequency of surveys will depend on each individual laboratory’s logistics,

time and personnel. A template (Lotus 123, Quatro or excel) to input data into the computer is available

from E.Weil. If you decide to carry on this protocol, please contact Dr. E. Weil at eweil@caribe.net.
37

Materials and Methods provided by D. Santavy (Santavy et al., 2001) for coral disease surveys

conducted in the Florida Keys.

General Approach

The SCUBA-based field study was developed and implemented over a two-year period in the

south Florida region. Survey areas were selected in the Lower Florida Keys in the vicinity of Key West,

the New Grounds, and the Dry Tortugas (Fig. 1). Zones that contained hard coral bottom were

demarcated within each geographic area. These coral reef zones were located using a prototype of the

Florida Marine Research Institute (FMRI) Benthic Habitats Map of the Florida Keys. Potential stations

for the pilot surveys were selected using a stratified random design, within the three regional areas. 

Individual stations were chosen by placing a random grid pattern that incorporated a hexagonal overlay

over the individual coral reef zones contained within each geographic area. Surveyors went to randomly

selected locations and assessed their suitability for sampling. If the location had sufficient coral coverage

(>5%), the site was surveyed; if it was not suitable, the next location on the list was assessed for

sampling suitability. Twenty-one stations were surveyed in the 1997 spring pilot survey.

Survey periods targeted late spring, the time when coral diseases are believed to emerge, and late

summer, the time when coral diseases are believed to be most prevalent. The 1997 spring and summer

pilot surveys were conducted during 1 to 8 June 1997 and 6 to14 September 1997. Stations assessed as

suitable during the spring pilot could not be permanently established at that time, but permission was

granted for permanent installation of stakes during the summer pilot. In September 1997, stations

assessed during the spring pilot were relocated using GPS coordinates, and permanent sites were

established by installing stakes to be used for future surveys in 20 of these stations (1 being omitted at

New Grounds). At the same time, 6 new stations were added in the Key West and Dry Tortugas areas. 

Survey strategy

Based on results from the 1997 pilot survey, reef type was added as a stratum to the 1998

sampling design (see Results). For the 1998 surveys, 6 additional stations were selected to balance the

sample design across two strata: (1) three geographic areas established in the pilot surveys and (2) three

reef types. The three reef types—fore reef, back reef, and transitional reef, as defined in the Florida

Keys National Marine Sanctuary (FKNMS) Management Document—were used for comparison among

the areas. However, not all areas contained all reef types; for example, only deep transitional reefs were

found in the New Grounds area. The 1998 spring survey was conducted from 25 May to 1 June 1998 and

the 1998 summer survey from 2 to 11 September 1998. Thirty-two stations were assessed in the spring

and summer of 1998. A power analysis was performed on the data acquired from both spring and

summer 1998 surveys to determine the optimal number of sampling stations and the appropriate " level

for data analysis. 

Survey methodology

All surveys were conducted using a radial arc transect method developed for this study. SCUBA

was used on deeper reefs and snorkel was used on shallow back reefs. A stainless steel rod was

positioned by driving it into the calcareous substratum for temporary sites (1997 spring pilot) or by

permanently affixing a 12" stainless steel pipe (all other surveys) at the designated site with underwater

epoxy (Gunnebo® Liquid Roc 500, Gunnebo Fastening Corporation 800-336-1640). Site coordinates

were determined by GPS technology during 1997, then by Differential-GPS (D-GPS) during 1998

surveys as it became available in our study region, improving our ability to easily locate stations. 

Surface maps with triangulation bearings and maps of underwater structures were generated, and a

subsurface 3" buoy was used to mark each station to enable us to return to each underwater stake. 

The survey procedure required inserting a 6-foot pole into the stainless steel pipe. The pole had

2 adjustable collets with a carabineer and a snap shackle on one end of the pole. A 12-m KevlarTM
38

fishing line contained within a plastic housing reel (fly-fishing reel) was fastened to the snap shackle on

the pole. The line was marked every meter and unreeled to desired lengths during the survey. Small

fluorescent tags attached to the line were used to mark the 2-m wide transect area under the line. A line

tender held the line taut above the reef structures and slowly moved the line in an arc around the fixed

central stake, allowing time for the surveyors to record their data (Fig 2). Two surveyors swam in

concentric circles directly over the line, one recording the number of colonies of each coral species and

the other recording the number of colonies of each species that displayed signs of a specific disease. The

surveyors counted colonies larger than 10 cm that fell directly below each 2-m segment of the line,

providing more than half of their area occurred within the segment. The originating point of the arc was

marked with a weighted subsurface buoy to alert the line tender when an entire arc segment had been

completed. 

During 1997, the surveys were conducted within the entire 10-m radius, in multiple radial

increments that enlarged the arc by 2 m for each complete circle. For example, the first arc segment

included the 0- to 2-m increment, the second arc segment included the 2- to 4-m segment, and so on until

the entire 10-m radius of the arc had been completed, circumscribing a total area of 314m2. A species

area curve was constructed to compare the June 1997 mean percent coral disease (MPCD) for increasing

increments of the radial arc areas within the arc transect. Analysis of variance was used to determine

whether the MPCD could be estimated using a portion of the arc, instead of the entire 10-m radius. 

Individual MPCD for each arc segment (0-2, then 2-4, and so on for each segment of 10-m radius) and

cumulative MPCD for the cumulative areas of the arc segments (0-2, then 0-4, and so on for the entire

10-m) were used for the analysis, with arc area used as the class variable. This investigation determined

that an area of 113m2, within the 8- to 10-m segment was sufficient for a reliable estimate of total MPCD

(see Results). Therefore, during 1998 surveys only the 8- to 10-m segment of the arc radius was used for

assessment.

Coral species and coral disease identification

Ten disease conditions affecting 16 species of scleractinian corals and gorgonian sea fans were

enumerated (Table 1). Three species of coral contained within the Montastraea annularis complex were

combined as a single category for data analysis,

because discrepancies in identification were noted

among some of the surveyors. Two gorgonian

species, Gorgonia flabellum and Gorgonia

ventalina, were combined as Gorgonia spp. All diseases

were scored only for colonies containing active

lesions; diseases were not scored if mortality had

occurred recently and the cause of death was not

apparent. Signs used to distinguish most coral diseases

have been detailed elsewhere (Table 1). Similar

conditions described in the literature as patchy necrosis

disease (Bruckner & Bruckner, 1997) and white pox

(Holden, 1996), might be the same disease. We could not distinguish between the two conditions based

on Bruckner & Bruckner’s (1997) mention of patchy necrosis or Holden’s (1996) mention of white pox;

therefore we used the term patchy necrosis disease/white pox to describe the lesions found on Acropora

palmata colonies that were not white-band disease or predation. We did not distinguish the differences

between white plague type 1 and 2, since the primary difference in distinguishing them in the literature is

dependent on the rate of progression (Dustan, 1977; Richardson et al., 1998a, 1998b). This could not be

determined in our surveys; therefore, we identified these conditions only as white plague in our surveys.

Finally, there is some uncertainty in identifying aspergillosis (Kim et al., 1997; Nagelkerken et al.,

1997a, 1997b; Smith et al., 1996). For our surveys, this disease was scored if one of the following
39

conditions were met: white fungal-like filaments with active lesions (tissue loss) and major skeletal

damage, or white fungal-like filaments with active lesions showing coenenchyme purpling, or white

fungal-like filaments with active lesions and purple galls in the vicinity of the diseased area. There are

some inconsistencies in the literature concerning the signs of this disease, therefore, one might prefer to

refer to the condition simply as sea fan disease. 

Quality assurance

A rigorous quality assurance (QA) plan was adopted to quantify surveyor error and minimize

data processing errors. The data collection protocols required training to improve identification skills

and familiarize participants with the survey procedures, including the completion of standardized data

forms. Scientific experts assessed the coral species and diseases in the 1997 surveys. Coral surveyors in

1998 were evaluated by expert coral taxonomists and expert coral pathologists for their ability to identify

coral species and to classify coral conditions as either healthy, affected by a specific disease, bleached, or

physically damaged. Only those individuals who had successfully passed a test (scoring 90% similarity

or greater using the experts as truth) were employed to collect data for the surveys. To evaluate intersurveyor error, we had multiple surveyors take repeated counts of coral colonies by species and of coral

disease types by species. To evaluate intra-surveyor error, we had each surveyor count species and

disease types multiple times at a single station. The QA plan included procedures for several levels of

data verification, including checks made in the field, duplicate surveys, and independent validation of all

electronically entered data. 

Data analysis

Data were recorded on standardized data sheets photocopied on Dura/CopyTM (J.L. Darling

Corp., Tacoma, WA.) underwater paper. All data were entered into a computerized database using a

PerForm ProTM-generated template, exported into MS Excel® worksheets, and used to create SAS data

sets. Electronic data quality was confirmed twice by someone other than the original data recorder. The

parameter of interest was mean percent coral disease (MPCD) (i.e., number of affected colonies per total

number of colonies) per unit area. Data were analyzed using one-way ANOVA for unbalanced design in

the 1997 pilot surveys and for balanced design in the 1998 surveys. The assumptions for ANOVA were

tested and met, including independence, homogeneity of variances, and normality. The class variables or

strata used included geographical areas (Key West, New Grounds, or Dry Tortugas) and reef types (back,

fore, or transitional reef). Statistical significance for type I error was designated as "=0.05 level. 

Tukey’s Studentized Range Test (HSD) was used for means separation at the " =0.05 level. A power

analysis was performed to determine appropriate type 1 and 2 errors, and statistical power to be

employed for future analyses. All analyses for the study were performed using SAS Version 6.12

(Statistical Analysis System Institute Inc., Cary, N.C., 1989-1996). 
40

Appendix II. Priorities for research on coral diseases linked to management objectives in

Florida. Developed by Brian Keller and Billy Causey.

1. Direct and indirect causes of coral decline in the Florida Keys, with emphasis on cause and

effect. Process-oriented research is required to separate natural variation in community

composition from anthropogenic changes. We know that disease contributes to the decline, but

we do not know its relative importance and how much forces such as global warming are adding

to the problem.

2. Effects of coral bleaching on coral survival. There is a general relationship between severity of

bleaching events and coral mortality. However, more information is needed on intra- and

interspecific differences in sensitivity to bleaching, habitat-related differences, and synergistic

effects, including possible genetic factors.

3. Coral pathology and epizootiology with an emphasis on cause and effect. More information is

needed on coral immune systems and how they may be compromised by environmental stresses,

whether a number of purported coral diseases meet Koch's criteria, how diseases spread, and

whether there are ways to prevent coral diseases.

4. Relationships between water quality and the incidence of diseases. There are claims that

elevated nutrient concentrations are associated with black-band disease.
41

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