NOAA TECHNICAL MEMORANDUM NOS NCCOS 156

May 2013

NOAA NCCOS Center for Coastal Monitoring and Assessment

An Assessment of Chemical Contaminants, Toxicity and 

Benthic Infauna in Sediments from the St. Thomas East 

End Reserves (STEER)

NOAA National Centers for Coastal Ocean Science

Center for Coastal Monitoring and Assessment

Anthony S. Pait

S. Ian Hartwell

Andrew L. Mason

Robert A. Warner

Christopher F.G. Jeffrey

Dennis A. Apeti

Simon J. Pittman

The Nature Conservancy

Anne M. Hoffman

The University of the Virgin Islands

Francis R. Galdo, Jr.

CH3
Acknowledgements

The authors wish to acknowledge the support from NOAA’s Coral Reef Conservation Program (CRCP) for this project. 

We would also like to thank Jean-Pierre Oriol, Director of the Department of Planning and Natural Resources (DPNR) 

Division of Coastal Zone Management, Roy Pemberton, Director along with Renata Platenberg and Stephen Hale of 

DPNR Division of Fish and Wildlife, Anita Nibbs of DPNR Division of Environmental Protection, Jeanne Brown of The 

Nature Conservancy, Tyler Smith, Sandra Romano, Kevin Brown, and Stanley Lateski of the University of the Virgin 

Islands (UVI), and Rob Ferguson and Marlon Hibbert of NOAA’s CRCP for help with the planning, logistics, and fi eld 

work along with interpretation of results for this project. Sybille Sorrentino of Virgin Island Ecotours graciously provided 

a base of operations for our fi eld work. We would also like to acknowledge the help provided by Alexandra Holecek and 

John Barimo, formerly of the DPNR Division of Coastal Zone Management and UVI, respectively. Finally, we would like 

to thank Captain Bobby Vante of the Bright Star for his skill and patience in getting us to the sampling sites within the St. 

Thomas East End Reserves.

Mention of trade names or commercial products does not constitute endorsement or recommendation for their 

use by the United States Government.

Citation

Pait, A.S., S.I. Hartwell, A.L. Mason, R.A. Warner, C.F.G. Jeffrey, A.M. Hoffman, D.A. Apeti, F.R. Galdo Jr., and S.J. Pittman. 2013. An assessment of chemical contaminants, toxicity and benthic infauna in sediments from the St. Thomas East 

End Reserves (STEER). NOAA Technical Memorandum NOS NCCOS 156. Silver Spring, MD. 70 pp.
1

NOAA/NOS/National Centers for Coastal Ocean Science

Center for Coastal Monitoring and Assessment (CCMA)

Coastal and Oceanographic Assessment, Status and Trends (COAST) Branch

1305 East/West Highway (SSMC-4, N/SCI-1)

Silver Spring, MD 20910

May 2013

2

The Nature Conservancy

St. Thomas, USVI

3

The University of the Virgin Islands

St. Thomas, USVI

NOAA Technical Memorandum NOS NCCOS 156

Anthony S. Pait1, S. Ian Hartwell1, Andrew L. Mason1, 

Robert A. Warner1

, Christopher F. G. Jeffrey1, Anne M. Hoffman2, 

Dennis A. Apeti1

, Francis R. Galdo Jr.3, and Simon J. Pittman1, 3

An Assessment of Chemical Contaminants, Toxicity and Benthic 

Infauna in Sediments from the St. Thomas East 

End Reserves (STEER)

United States Department 

of Commerce

Rebecca Blank

Deputy Secretary 

National Oceanic and Atmospheric 

Administration

Kathryn Sullivan

Acting Under Secretary

National Ocean Service

Holly Bamford

Assistant Administrator
Table of Contents

Abstract .............................................................................................................................................. 1

Introduction ........................................................................................................................................ 1

 STEER Boundaries ................................................................................................................... 2

 Aquatic Environment ................................................................................................................ 2

 Mangroves ............................................................................................................................ 2

 Seagrass Beds ....................................................................................................................... 2

 Coral Reefs ........................................................................................................................... 3

 Interconnected Habitats ........................................................................................................ 3

 Watersheds ................................................................................................................................ 3

 NOAA/NCCOS Involvement in the STEER ............................................................................ 4

 Sediment Quality Triad ............................................................................................................. 4

 Overview of the Chemical Contaminants ............................................................................. 5

 Sediment Toxicity Tests ........................................................................................................ 6

 Benthic Infaunal Analysis ..................................................................................................... 7

Materials and Methods ....................................................................................................................... 7

 Samples for Chemical Contaminant Analysis .......................................................................... 9

 Sampling Protocols ................................................................................................................... 9

 Statistical Analysis .................................................................................................................... 9

 Samples for Sediment Toxicity Bioassays .............................................................................. 11

 Amphipod Toxicity Test .......................................................................................................... 11

 Sea Urchin Fertilization Test .................................................................................................. 11

 P450 Test ................................................................................................................................. 11

 Benthic Infaunal Analysis ....................................................................................................... 12

Results and Discussion .................................................................................................................... 14

 Field Data ................................................................................................................................ 14

 Total Organic Carbon and Grain Size ..................................................................................... 15

 Chemical Contaminants .......................................................................................................... 15

 Polycyclic Aromatic Hydrocarbons .................................................................................... 15

 Total Extractable Hydrocarbons ......................................................................................... 18

 Aliphatics ............................................................................................................................ 19

 Polychlorinated Biphenyls .................................................................................................. 19

 DDT and Other Organochlorine Pesticides ........................................................................ 20

 Tributyltin (TBT) ................................................................................................................ 22

 Cadmium ............................................................................................................................. 25

 Chromium ........................................................................................................................... 26

 Copper ................................................................................................................................. 27

 Lead .................................................................................................................................... 29

 Mercury ............................................................................................................................... 30

 Nickel .................................................................................................................................. 31

 Zinc ..................................................................................................................................... 32

 Normalization of Trace Elements ....................................................................................... 33

 Clostridium perfringens ...................................................................................................... 35

 Sediment Toxicity ................................................................................................................... 36

 Amphipod Toxicity ............................................................................................................. 37

 Sea Urchin Fertilization ...................................................................................................... 37

 P450 .................................................................................................................................... 37

ii
 Benthic Community Analysis ................................................................................................. 38

 Nodal Analysis .................................................................................................................... 40

 SIMPER Analysis ............................................................................................................... 41

 Overall Patterns in the STEER Benthic Community .......................................................... 43

 Infl uence of Chemical Contaminants on the Benthic Infaunal Community ....................... 44

Summary and Conclusions .............................................................................................................. 44

Literature Cited ................................................................................................................................ 47

Appendices ....................................................................................................................................... 51

 Appendix A. Field data collected from the STEER 2011 mission ......................................... 51

 Appendix B. Grain size and organic carbon of sediments from St. Thomas East 

 End Reserves ........................................................................................................................... 52

 Appendix C. PAHs detected in sediments from the St. Thomas East End 

 Reserves (ng/ dry g) ................................................................................................................ 53

 Appendix D. Aliphatics and total extractable hydrocarbons from the St. Thomas 

 East End Reserves ................................................................................................................... 56

 Appendix E. PCBs detected in the sediments from the St. Thomas East End Reserves ........ 59

 Appendix F. Organochlorine compounds detected in sediments from the St. 

 Thomas East End Reserves (ng/dry g) .................................................................................... 62

 Appendix G. Butyltins detected in sediments from the St. Thomas East End 

 Reserves (ng Sn/dry g) ............................................................................................................ 65

 Appendix H. Major and trace elements detected in sediments from St. Thomas 

 East End Reserves (μg/dry g) ................................................................................................. 66

 Appendix I. Trace elements plotted against aluminum and calcium ..................................... 68

 Appendix J. Clostridium perfringens in sediments from the St. Thomas East 

 End Reserves ........................................................................................................................... 70

Table of Contents (continued)

iii
List of Tables

Table 1. Compounds analyzed in sediments from the St. Thomas East End Reserves ................ 10

Table 2. Comparison of higher concentrations of individual PAHs at STEER sites with 

 NOAA NS&T data .......................................................................................................... 17

Table 3. Comparison of higher concentrations of pesticides at STEER sites with 

 NOAA NS&T data .......................................................................................................... 21

Table 4. Toxicity bioassay summary results from the STEER ..................................................... 36

Table 5. Average (n = 3) P450 bioassay response following 6 and 24 hour incubation with 

 STEER sediment extracts ............................................................................................... 37

Table 6. Spearman Rank correlation coeffi cients (bold) and signifi cance level for 

 community parameters and selected physical and chemical parameters, and 

 toxicological results ........................................................................................................ 41

Table 7. Results of SIMPER analysis. Species highlighted in green were cosmopolitan and 

 were found in all strata. Species highlighted in yellow were found in Strata 1 and 2 ... 41

Table 8. Top species in each stratum. Taxa highlighted in green were cosmopolitan and 

 were found in all strata. Species highlighted in blue were found in 

 Strata 3, 4, and 5 ............................................................................................................. 43

Table 9. Average per-station abundance of selected taxonomic groups in Mangrove 

 Lagoon and Benner Bay without stations 1-4P and 2-19P, stations 1-4P and 

 2-19P together, and the remaining strata in 3 ( Nazareth Bay), 4 ( Cowpet/

 St. James Bay), and 5 (Great Bay) ................................................................................. 44

iv
List of Figures

Figure 1. Individual Reserves that comprise the STEER ................................................................... 2

Figure 2. Primary watersheds adjacent to the STEER ....................................................................... 3

Figure 3. Strata and sediment sites sampled in the St. Th omas East End Reserves (STEER) 

 in June 2011 ............................................................................................................................ 8

Figure 4. Combined cluster analysis overlays of species clusters and site clusters. The top 

 fi gure illustrates the dominant species communities found in different site 

 clusters. The lower fi gure illustrates how different species assemblages 

 distribute themselves between different habitats ..........................................................13

Figure 5. Hypothetical representation of the distribution of physicochemical habitat 

 parameters, contaminant concentrations, and other site-specifi c data used to 

 characterize site and species clusters ............................................................................14

Figure 6. Percent fi nes (percent silt plus percent clay fractions) in sediments from 

 the STEER ............................................................................................................................... 15

Figure 7. Total polycyclic aromatic hydrocarbons (PAHs) detected in sediments from 

 the St. Thomas East End Reserves ...............................................................................16

Figure 8. Total extractable hydrocarbons (TEH) detected in sediments from the St. Thomas 

 East End Reserves ........................................................................................................18

Figure 9. Straight chain and branched hydrocarbons (aliphatics) in sediments from the St. 

 Thomas East End Reserves ..........................................................................................19

Figure 10. Total PCBs detected in sediments from the St. Thomas East 

 End Reserves ................................................................................................................19

Figure 11. Total DDT detected n sediments from the St. Thomas East End Reserves ..................21

Figure 12. Tributyltin detected in sediments from the St. Thomas East End Reserves. 

 BB-1 and BB-2 represent targeted, nonrandomized samples taken in 2010 ................23

Figure 13. Tributyltin detected in sediments from southwest Puerto Rico and 

 Vieques, Puerto Rico. Values represent means ............................................................24

Figure 14. Tributyltin detected in sediments from three sites in the STEER ...............................24

Figure 15. Cadmium detected in sediments from the St. Thomas East End Reserves ..................26

Figure 16. Chromium detected in sediments from the St. Thomas East End Reserves .................27

Figure 17. Copper detected in sediments from the St. Thomas East End Reserves ......................28

Figure 18. Lead detected in sediments from the St. Thomas East End Reserves ..........................29

Figure 19. Mercury detected in sediments from the St. Thomas East End Reserves ....................30

Figure 20. Nickel detected in sediments from the St. Thomas East End Reserves .......................31

Figure 21. Zinc detected in sediments from the St. Thomas East End Reserves ...........................32

Figure 22. Normalization of aluminum to %fi nes (a), aluminum to iron (b), aluminum to 

 chromium (c), and calcium to chromium (d) in sediments from the STEER ..............33

Figure 23. Normalization of aluminum to calcium (a), aluminum to copper (b), aluminum 

 to zinc (c), and aluminum to mercury (d) in sediments from the STEER ....................34

Figure 24. Clostridium perfringens detected in sediments from the St. Thomas East 

 End Reserves ................................................................................................................35

Figure 25. Amphipod mortality vs % sand and gravel in St. Thomas STEER sediments ............36

Figure 26. Amphipod mortality versus % total organic carbon in the STEER sediments............36

Figure 27. P450 response vs PAH concentrations (a), P450 response in terms of B[a]P eq 

 for the subset of samples that exceeded the TCDD standard response (b) ..................37

Figure 28. P450 response (normalized to standard 10nM TCDD) following 6 and 24 hour 

 exposures to extracts from St. Thomas STEER sediment samples. (QA/QC 

 samples; blank=solvent blank; clean=uncontaminated site in Chesapeake Bay; 

 contam.=contaminated site in Chesapeake Bay; spiked solvent solution) ...................38

v
Figure 29. Distribution of bioassays showing responses that were signifi cantly different 

 than controls or greater than a standard threshold (P450) in St. Thomas 

 STEER sediments .........................................................................................................39

Figure 30. Plot of total abundance of each species used in the analyses. Each triangle 

 represents the total abundance of each individual species collected in the STEER .....39

Figure 31. Total animal abundance at each station in the STEER .................................................40

Figure 32. Total number of species (taxa) and calculated diversity at each station in 

 the STEER ....................................................................................................................40

Figure 33. Results of the SIMPER analysis for Strata 1-2 ............................................................42

Figure 34. Results of the SIMPER analysis for Strata 3-5 ............................................................42

Figure 35. Relationship between number of species and species diversity and the ERMq ...........44

Figure 36. Relationship between number of species and species diversity and 

 percent silt + clay .........................................................................................................45

Figure 37. Relationship between mean ERMq and percent silt + clay ..........................................45

vi

List of Figures (continued)
STEER Sediment Contaminants and Bioeffects Report

Introduction

1

Abstract

This report contains a chemical and biological characterization of sediments from the St. Thomas East End 

Reserves (STEER) in St. Thomas, U.S. Virgin Islands 

(USVI). The STEER Management Plan (published in 

2011) identifi ed chemical contaminants and habitat loss 

as high or very high threats and called for a characterization of chemical contaminants as well as an assessment of 

their effects on natural resources. The baseline information contained in this report on chemical contaminants, 

toxicity and benthic infaunal community composition can 

be used to assess current conditions, as well as the effi -

cacy of future restoration activities. 

In this phase of the project, 185 chemical contaminants, 

including a number of organic (e.g., hydrocarbons and 

pesticides) and inorganic (e.g., metals) compounds, 

were analyzed from 24 sites in the STEER. Sediments 

were also analyzed using a series of toxicity bioassays, 

including amphipod 

mortality, sea urchin 

fertilization impairment, and the cytochrome P450 Human 

Reporter Gene System 

(HRGS), along with 

a characterization of 

the benthic infaunal 

community. 

Higher levels of 

chemical contaminants were found in 

Mangrove Lagoon 

and Benner Bay in 

the western portion 

of the study area than 

in the eastern area. 

The concentrations 

of polychlorinated biphenyls (PCBs), DDT (dichlorodiphenyltrichloroethane), chlordane, zinc, copper, lead and 

mercury were above a NOAA sediment quality guideline 

at one or more sites, indicating impacts may be present in more sensitive species or life stages in the benthic 

environment. Copper at one site in Benner Bay, however, 

was above a NOAA guideline indicating that effects on 

benthic organisms were likely. The antifoulant boat hull 

ingredient tributyltin, or TBT, was found at the third 

highest concentration in the history of NOAA’s National 

Status and Trends (NS&T) Program, which monitors 

the Nation’s coastal and estuarine waters for chemical 

contaminants and bioeffects. Unfortunately, there do not 

appear to be any established sediment quality guidelines 

for TBT. Results of the bioassays indicated signifi cant 

sediment toxicity in Mangrove Lagoon and Benner Bay 

using multiple tests. The benthic infaunal communities 

in Mangrove Lagoon and Benner Bay appeared severely 

diminished. 

Introduction

The St. Thomas East End Reserves, or STEER, is a collection of Marine Reserves and Wildlife Sanctuaries (MRWS) 

located on the southeastern end of the island of St. Thomas, 

U.S. Virgin Islands (Figure 1). Within the STEER, there 

are extensive mangroves and seagrass beds, along with coral reefs, lagoons and cays. The value of the natural resources in the Reserves has long been recognized. In 1979, the 

area was identifi ed by NOAA’s National Marine Sanctuary 

Program as a “marine area of national signifi cance, deserving of marine sanctuary designation” (NOAA, 1981). The 

same year, the Mangrove Lagoon/Benner Bay area, along 

with Vessup Bay, were designated by the USVI government 

as Areas of Particular Concern, or APC, 

due to the abundance 

of important but 

threatened natural 

resources, and the 

desire to preserve 

and, as needed, restore these areas.

The STEER is made 

up of four MRWS, 

including the Inner 

Mangrove Lagoon, 

Cas Cay/Mangrove 

Lagoon, St James, 

and Compass Point 

Salt Pond Marine 

Reserves and Wildlife 

Sanctuaries (Figure 

1). In 2008, the U.S. Virgin Islands Department of Planning 

and Natural Resources (DPNR) received a permit application for a fl oating bar and restaurant that would be located 

in the St. James MRWS. Public opposition to this proposed 

activity was strong, but a review of existing regulations at 

the time did not show the activity was specifi cally prohibited. As a result of this episode, along with recognition 

of the connectivity of the natural, cultural, and economic 

resources of the four Reserves, it was decided that a 

comprehensive management plan was needed, in order to 

protect and properly manage the natural resources in the 

area (STEER, 2011). In April 2008, DPNR along with the 

University of the Virgin Islands, The Nature Conservancy, 

View into the St. Th omas East End Reserves (STEER). R
Introduction

2

STEER Sediment Contaminants and Bioeffects Report

and a community group called the Friends of Christmas 

Cove, formed the STEER Core Planning Group and began 

development of a management plan for the STEER, which 

was completed in May 2011. 

STEER Boundaries

The STEER comprises an area of approximately 9.6 km2

, 

with approximately 34 km of coastline (STEER, 2011). 

Boundaries for the STEER include the Mangrove Lagoon/

Benner Bay MRWS with Long Point as the western border 

(Figure 1). The St. James MRWS forms the eastern boundary of the STEER, which includes the waters surrounding 

Great St. James and the north shore of Little St. James Island. To the north, the boundary of the STEER runs along 

the coastline, from Cabrita Point westward to Benner Bay. 

At Benner Bay, the boundary follows a line offshore from 

Coculus Rock along Roto Cay to the northeastern entrance 

of Mangrove Lagoon; the marina areas within Benner Bay 

are outside of the STEER. 

Aquatic Environment

With mangroves, seagrass beds, lagoons, salt ponds, coral 

reefs and a number of cays, the STEER contains a multitude of habitats and natural resources. The STEER is 

thought to be one of the most valuable nursery areas remaining in St. Thomas, with many species of fi sh and shellfi sh spending some portion of their lives in the protected 

areas around the mangroves and in the extensive seagrass 

beds (STEER, 2011). Fishing is not allowed in most parts 

of the Reserves, and where it is allowed (e.g., for baitfi sh), 

a DPNR permit is required. 

The abundance of natural resources has contributed to 

the STEER being a popular destination for recreational 

activities, ranging from swimming, camping, snorkeling 

and SCUBA, to boating and ecotourism. These uses have 

recently been documented in a coastal use mapping project for the STEER funded by NOAA’s CRCP (Dillard and 

D’lorio, 2012).

Mangroves. The largest mangrove system in St. Thomas 

occurs along the shores of Mangrove Lagoon/Benner Bay 

(IRF 1993). Mangrove species include the red mangrove 

(Rhizophora mangle), black mangrove (Avicennia germinans), and white mangrove (Laguncularia racemosa). 

Mangroves offer many ecological benefi ts. They serve as 

natural buffers against shore erosion, fl oods and hurricane 

waves. Mangroves also provide protection for juvenile 

fi sh and other organisms around the roots, and generate 

detrital material that enters the food chain, becoming a food 

resource for a number of marine organisms (DPNR-DFW, 

2005). Sampling with fi sh traps along the mangrove fringe 

in Benner Bay/Mangrove Lagoon has yielded as many as 

40 fi sh species (Boulon, 1992; Colletti 2011). 

Seagrass Beds. There are extensive areas of seagrass in 

Benner and Jersey Bays. At one time, seagrasses were also 

abundant in Mangrove Lagoon (Grigg et al., 1971). Turtle 

Figure 1. Individual Reserves that comprise the STEER. 

Cas Cay/Mangrove Lagoon

St. Thomas, USVI

Mangrove 

Lagoon

St. James 

Bay

Benner Bay

Jersey Bay

Great Bay

Cowpet

Bay

Inner Mangrove Lagoon

St. James

Compass Point Salt Pond

Bovoni 

Landfill

Turpentine 

Gut

Patricia Cas Cay

Cay

Coculus 

Rock Roto

Cay

Deck 

Point

Cabrita 

Point

Little St. 

James

Great St. 

James

Long

Point
STEER Sediment Contaminants and Bioeffects Report

Introduction

3

grass (Thalassia testudinum) and manatee grass (Syringodium fi liforme) are two of the major seagrass species found 

in the STEER (DPNR-DFW, 2005). Seagrasses provide 

habitat for many organisms, including juvenile fi sh. Seagrasses are also an important food source for parrotfi sh, 

surgeonfi sh, and pinfi sh, along with turtles, birds, and sea 

urchins. Conch feed off the epiphytes on the seagrass 

leaves (DPNR-DFW, 2005). Finally, seagrasses in the Caribbean, as in other areas, help to improve water clarity and 

light penetration, by trapping fi ne sediments and allowing 

the sediment particles to settle out of the water column. 

Coral Reefs. There are signifi cant coral reef areas in Jersey 

Bay and also south of Cas and Patricia Cays. Many species 

of coral can be found in the STEER, including the star coral 

complex (Montastraea annularis, M. faveolata and M. 

franksi), mustard hill coral (Porites astreoides), lesser and 

massive starlet corals (Siderastrea radians and S. siderea),

fi nger coral (P. porites), 

symmetrical brain coral 

(Diploria strigosa), and 

great star coral M. cavernosa (DPNR-DFW, 

2005). Also within the 

STEER are the threatened elkhorn (Acropora 

palmata) and staghorn (A. 

cervicornis) corals. The 

STEER is a relatively 

shallow system, supporting both patch and fringing reefs. The coral reefs 

provide habitat and food 

for many organisms. 

Interconnected Habitats. 

Not surprisingly, the 

habitats in the STEER 

are closely linked to 

one another. For example, a variety of fi sh and invertebrates move between 

the mangroves, seagrass beds and coral reefs, either during 

the course of their lives (e.g., juvenile fi sh living among 

the mangrove prop roots for protection, with adults moving out onto the reefs), or as part of a diurnal cycle (e.g., 

invertebrates and fi sh feeding in the seagrass beds at night 

and returning to the protection of the reefs during the day) 

(STEER, 2011). 

Degraded environmental quality in any one of these habitats affects the others. Poor water and sediment quality in 

mangrove areas will reduce habitat quality for fi sh species 

and their prey, particularly those sensitive to dissolved oxygen concentrations. Elevated levels of suspended sediment 

in the water column can lead to a reduction in the amount 

of light reaching seagrasses and corals, which can result in 

reduced growth or even die-off. Sediments that settle out 

of the water column can also act to smother corals. Elevated nutrient levels can result in increased algal growth 

in the water column and, as with sediments, can reduce the 

amount of light reaching corals or seagrasses. Chemical 

contaminants can impact a variety of organisms and life 

stages. Excess nutrients also promote the growth of epiphytic algae that may smother coral and seagrass. 

Watersheds

There are two watersheds which drain into the STEER, 

the Jersey Bay and the Red Hook watersheds (Figure 2). 

The largest is the Jersey Bay watershed which empties 

into Mangrove Lagoon/Benner Bay and Jersey Bay. The 

Frenchman Bay watershed drains to the west 

of the STEER. The 

area of the STEER east 

of Deck Point receives 

input from the Red 

Hook watershed. It has 

been estimated that 

approximately onethird of the population 

of the island of St. 

Thomas resides in the 

Mangrove Lagoon/

Benner Bay APC or 

Area of Particular 

Concern (IRF, 1993). 

There are a multitude 

of land uses within 

the watersheds that 

drain into the STEER, 

including a large active landfi ll, numerous marinas and boatyards, a number 

of resorts, various commercial/industrial activities, an EPA 

Superfund Site, a horse racetrack, and residential areas 

served by individual septic systems, some of which are 

likely failing (IRF, 1993). The EPA Superfund site (Tutu 

Wellfi eld Superfund Site) was established due to contamination of groundwater and wells in the area by chlorinated 

volatile organic compounds (CVOC) (EPA, 2011). All of 

these watershed activities have the potential to contribute 

both point and nonpoint source pollution to the STEER. 

The area that borders the western side of Mangrove Lagoon 

contains the Bovoni Landfi ll, which serves not only all of 

Jersey Bay 

Watershed Red Hook 

Bay 

Watershed

STEER

Figure 2. Primary watersheds adjacent to the STEER. 

Frenchman

Bay 

Watershed
Introduction

4

STEER Sediment Contaminants and Bioeffects Report

St. Thomas, but also receives solid waste from St. John. 

The landfi ll covers approximately 330 acres, with nearly 40 

acres directly adjacent to Mangrove Lagoon (IRF, 1993). 

On the northern side of Mangrove Lagoon is the Clinton 

Phipps Racetrack. During construction of the racetrack, the 

mangrove delta draining Turpentine Gut, the only perennial 

stream on St. Thomas (Nemeth and Platenberg, 2007), was 

altered by fi lling and diverting the delta to form a single 

channel, resulting in additional sediment being deposited 

directly into Mangrove Lagoon rather than in the delta 

(STEER, 2011). 

There are also numerous marinas in Benner Bay, serving 

both residents and transient boaters. There are signifi cant 

residential areas in the Jersey Bay watershed and, along 

the north shore of Jersey and Cowpet Bays, a number of 

resorts/hotels, condominiums and yacht clubs. 

Elevated levels of chemical contaminants have been 

documented in the STEER watershed (EPA, 2011). DPNR 

has said that the extent of chemical contamination and 

biological effects or bioeffects in the STEER are currently 

unknown, but that data on land-based sources of pollution are needed in order to make better informed decisions 

on coastal resource management. The quantifi cation of 

sediment contaminants, toxicity, and the benthic infaunal 

community, along with the biological survey being conducted as part of this project, are helping to provide the 

data needed to optimize management of the STEER.

NOAA/NCCOS Involvement in the STEER

At the NOAA Coral Reef Ecosystem Integrated Observing System (CREIOS) Meeting in San Juan, Puerto Rico 

in 2009, NOAA scientists met with resource managers and 

local scientists from the U.S. Caribbean, including representatives from the Virgin Islands, to elicit priority information needs, and to highlight important issues of concern. 

At that meeting, representatives from DPNR’s Divisions 

of Coastal Zone Management and Environmental Protection identifi ed the STEER as a priority area, and noted that 

there were signifi cant data and information gaps in terms 

of the chemical contaminants present, their concentrations, 

effects, and the overall health of the biological communities 

within the STEER. 

With these needs in mind, NOAA’s National Centers for 

Coastal Ocean Science (NCCOS), in partnership with the 

STEER Core Planning Group consisting of scientists and 

managers from DPNR’s Divisions of Coastal Zone Management, Fish and Wildlife, and Environmental Protection, along with the University of the Virgin Islands, and 

The Nature Conservancy, proposed a multiyear project to 

NOAA’s Coral Reef Conservation Program (CRCP), to develop an integrated assessment of chemical and biological 

conditions within the STEER. In 2011, NCCOS scientists 

along with project partners collected sediments for chemical contaminant analysis, toxicity bioassays, and benthic 

infaunal analysis. As part of the work in Year 1, the University of the Virgin Islands also began monthly sampling 

for nutrients, and monthly monitoring of total suspended 

solids (TSS, a CRCP performance measure), and sedimentation, using sediment traps placed at fi ve locations within 

the STEER. Passive water samplers, or POCIS, were also 

deployed in the same locations as the sediment traps. The 

passive water samplers are used to quantify the presence of 

wastewater contaminants in the water column. Activities 

in the second year included a biological survey of the entire 

STEER, along with the collection of coral and conch for 

chemical contaminant analysis, and the continued monthly 

monitoring of nutrients, TSS, and the sediment traps. The 

results of the Year 2 and other assessment activities (e.g., 

POCIS) will be included in additional project publications. 

In another CRCP-funded project, the goal of which is to 

develop a watershed management plan for the STEER, 

a number of these and other watershed issues are being 

highlighted, along with opportunities, goals, and actions 

needed. Reducing the impacts from the landfi ll, along with 

the need for improving wastewater and storm water management, pollution prevention, and wetland restoration, 

are seen as key items for the STEER watershed restoration 

(Kitchell, 2012).

In addition to the chemical and biological analysis, 

NOAA’s CRCP also funded an effort to develop a new high 

resolution map describing the distribution, quantity and 

type of seafl oor habitats inside the STEER. This map is being developed from LiDAR (Light Detection and Ranging)

bathymetry and refl ectivity imagery collected by Fugro 

LADS and the U.S. Geological Survey. The new habitat 

map and related products will be used to update nautical 

charts in the area to: help fi ll critical information gaps about 

the seafl oor in a priority area identifi ed by NOAA’s CRCP; 

support fi sheries-related performance measures outlined in 

the USVI Jurisdictional Working Group Priority Settings 

document; and to support best management practices inside 

the STEER, related to permitting activities, restoration, 

fi sheries, climate change and scientifi c research.

Sediment Quality Triad

This report covers the results of the chemical contaminant 

analysis in sediments, sediment bioassays, and benthic 

infaunal analysis from Year 1 of the project in the STEER. 

These three components make up what is referred to as 
STEER Sediment Contaminants and Bioeffects Report

Introduction

5

the Sediment Quality Triad (SQT). The SQT has been 

developed to assess the presence and impacts of chemical 

contaminants in benthic habitats (Chapman et al., 1987). 

Additional information on each of these three components 

follows.

Overview of the Chemical Contaminants. The quantifi cation of chemical contaminants in sediments provides the 

opportunity for understanding what chemical stressors are 

present, their concentrations, 

how these concentrations compare to established sediment 

quality guidelines, along with 

providing input to the other 

two components of the triad. 

Each of the contaminant classes 

analyzed for this project are 

discussed below. 

Polycyclic Aromatic Hydrocarbons. Also referred to as PAHs, 

polycyclic aromatic hydrocarbons are associated with the use 

and combustion of fossil fuels 

(e.g., oil and gas) and other 

organic materials (e.g., wood 

and trash). Natural sources of PAHs include forest fi res, 

and the decay of vegetation. The PAHs analyzed are two 

to six ring aromatic compounds. An example of a three 

ring PAH (1-methylphenanthrene) is shown on the cover 

of this report. A number of PAHs bioaccumulate in aquatic 

and terrestrial organisms, are toxic, and some including 

benzo[a]pyrene, benz[a]anthracene, chrysene, benzo[b]

fl uoranthene, benzo[k]fl uoranthene, dibenzo[a,h]anthracene, and indeno[1,2,3-c,d]pyrene, are likely carcinogens 

(USDHHS, 1995). 

Aliphatic Hydrocarbons. In addition to the PAHs, another 

group of hydrocarbons, the aliphatics were analyzed in the 

sediments. Aliphatic hydrocarbons are straight chain or 

branched nonaromatic structures. Aliphatic hydrocarbons 

are often associated with uncombusted fuels such gasoline, 

diesel or oil. 

Polychlorinated Biphenyls. Commonly referred to as 

PCBs, polychlorinated biphenyls are synthetic compounds 

that have been used in numerous applications ranging from 

electrical transformers and capacitors, to hydraulic and heat 

transfer fl uids, to pesticides and in paints. Approximately 

60 percent of PCBs manufactured in the U.S. were used in 

electrical applications (EPA, 1997). PCBs have a biphenyl 

ring structure (two benzene rings with a carbon to carbon 

bond) and a varying number of chlorine atoms. There are 

209 PCB congeners possible. 

PCBs were manufactured in the U.S. between 1929 and 

1977. In the United States, all PCBs were produced by a 

single manufacturer, and the commercial products were 

referred to as Aroclors. Aroclors are mixtures of PCB 

congeners. The manufacture of PCBs in the U.S. was 

banned in 1979 due to their toxicity. Because PCBs bioaccumulate and degradation in 

the environment proceeds only 

slowly, they are now ubiquitous contaminants. Exposure 

to PCBs in fi sh has been linked 

to reduced growth, reproductive impairment and vertebral 

abnormalities (EPA, 1997). 

Organochlorine Pesticides. 

Beginning in the 1950s and 

continuing in to the early 

1970s, a series of chlorine 

containing hydrocarbon insecticides were used to control 

mosquitoes and agricultural 

pests. One of the best known 

of the organochlorine pesticides was the insecticide DDT 

(dichlorodiphenyltrichloroethane). 

The use of many of the organochlorine pesticides, including 

DDT, was banned due to their environmental persistence, 

potential to bioaccumulate, and especially the chronic 

(i.e., longer-term) effects on nontarget organisms. Organochlorine pesticides are typically neurotoxins, and DDT 

along with PCBs have also been shown to interfere with 

the endocrine system. DDT and its metabolite DDE, for 

example, were specifi cally linked to eggshell thinning in 

birds, particularly raptors, but also in pelicans. A number 

of organochlorine pesticides are toxic to nontarget aquatic 

life as well, including crayfi sh, shrimp and some species of 

fi sh. While DDT was banned by the EPA for most uses in 

the U.S. in 1972, it is still effectively used in some developing countries, particularly on the inside of living areas to 

help control mosquitos that can transmit malaria. 

Most uses of the organochlorine insecticide chlordane were 

canceled in 1978, and all uses were canceled by 1988. A 

primary non-agricultural use of chlordane was in the treatment of wooden structures to prevent damage by termites. 

Because of their persistence and heavy use in the past, residues of organochlorine pesticides can also be found in the 

environment, including in biota. The persistence of these 

c

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Th e Bovoni Landfi ll on the western end of the STEER receives solid waste t

from both St. Th omas and St. John. 
Introduction

6

STEER Sediment Contaminants and Bioeffects Report

compounds and toxicity to nontarget organisms continues 

to be an environmental concern.

Butyltins. This compound class has a range of uses, from 

biocides to catalysts to glass coatings. In the 1950s, tributyltin, or TBT, was fi rst shown to have biocidal properties 

(Bennett, 1996). In the late 1960s, TBT was incorporated 

into an antifoulant paint system, quickly becoming one of 

the most effective paints ever used on boat hulls (Birchenough et al., 2002). TBT was 

incorporated into a polymer paint 

system that released the biocide 

at a constant and minimal rate, to 

control fouling organisms such 

as barnacles, mussels, weeds, and 

algae (Bennett, 1996). 

TBT was linked to endocrine 

disruption, specifi cally an imposex 

(females developing male characteristics) condition in marine gastropods, and in other mollusks (e.g., 

oysters), abnormal shell development, and poor weight gain (Batley, 

1996). Beginning in 1989, the use of TBT as an antifouling 

agent was banned in the U.S. on non-aluminum vessels 

smaller than 25 meters in length (Gibbs and Bryan, 1996). 

In a survey of TBT in the USVI, Strand et al. (2009) found 

evidence of elevated levels of TBT and its degradation 

products in gastropod species, as well as imposex organisms at several locations, including the harbor in Charlotte 

Amalie Bay, St. Thomas. 

In the aquatic environment, TBT is degraded by microorganisms and sunlight (Bennett, 1996). The transformation 

involves sequential debutylization resulting in dibutyltin, 

monobutyltin, and fi nally inorganic tin (Batley, 1996). 

Major and Trace Elements. All of the major and trace 

elements occur naturally to some extent in the environment. Aluminum, iron, and silicon are major elements in 

the Earth’s crust. As their name implies, trace elements 

occur at lower concentrations in crustal material, however, 

mining and manufacturing processes along with the use and 

disposal of products containing trace elements can lead to 

elevated concentrations in the environment. 

A number of trace elements are toxic at low concentrations. Cadmium, used in metal plating and solders, has 

been shown to impair development and reproduction in 

several invertebrate species, and osmoregulation in herring 

larvae (USDHHS, 1999; Eisler, 1985). Mercury is volatile 

and can enter the atmosphere through processes including 

mining, manufacturing, combustion of coal and volcanic 

eruptions (Eisler, 1987). Mercury is currently used in compact and other fl uorescent light bulbs, electrical switches 

and relays, thermostats and in some dental amalgams. Effects of mercury on copepods include reduced growth and 

rates of reproduction (Eisler, 1987). Chromium has been 

shown to reduce survival and fecundity in the cladoceran 

Daphnia magna, and reduced growth in fi ngerling chinook 

salmon (Oncorhynchus tshawytscha) (Eisler, 1986). Copper has 

a number of uses, such as in 

antifouling paints for boats, wood 

preservatives, heat exchangers 

in power plants, electrical wires, 

coinage, and in agricultural fungicides. While an essential biological element, elevated levels of 

copper can impact aquatic organisms, including the functioning 

of gills along with reproduction 

and development (Eisler, 1998). 

Most of the current uses of lead 

appear to be in lead-acid batteries, 

although other uses include oxides in glass and ceramics. 

In the past, lead was used in paints and also in gasoline, 

however, these uses have ended due to environmental and 

human health concerns. Nickel has many applications in 

both industrial and consumer products. Approximately 

65% of the nickel in the U.S. is used to make stainless steel. 

Other uses include its incorporation into a series of alloys, 

in rechargeable batteries (Ni-Cd), catalysts, coins, plating, 

and in foundry products. Corrosion-resistant zinc plating 

of steel (hot-dip galvanization) is an important application, accounting for roughly 50% of zinc use. In the marine 

industry, zinc anodes are used to protect vital engine and 

boat parts (e.g., propellers, struts, rudders, and outboard 

and inboard engines), and is a component in some antifoulant paint formulations. Zinc is also used in batteries, and in 

alloys such as brass. 

Bacterial Indicator. Although not a chemical contaminant, 

the bacterium Clostridium perfringens has been used as an 

indicator of fecal pollution and was analyzed in the sediment samples from the STEER. This bacterium occurs in 

the intestines of humans and in some domestic and feral 

animals, and is a common cause of food poisoning.

Sediment Toxicity Tests. NOAA’s NCCOS, National Status and Trends Bioeffects Program routinely uses a suite of 

tests to assess sediment toxicity through different modes of 

contaminant exposure (bulk sediment, sediment porewater, 

Marina area in Benner Bay. 
STEER Sediment Contaminants and Bioeffects Report

Materials and Methods

7

and chemical extracts of contaminants from sediment) to a 

variety of species (invertebrates, vertebrate cells and bacteria) and different assessment end-points (i.e., mortality, 

impaired reproduction, physiological stress, and enzymatic 

response). 

Since the test results are not necessarily axiomatic and 

biological effects of contaminants occur at different levels 

of biological organization, i.e., from cells to ecosystems, 

results from a suite of toxicity tests are used in the “weight 

of evidence” context to infer the incidence and severity of 

environmental toxicity (Chapman, 1996). The toxicity bioassays used in this project included amphipod (Ampelisca 

abdita) mortality, sea urchin (Arbacia punctulata) fertilization impairment, and cytochrome P450 Human Reporter 

Gene System (HRGS).

Benthic Infaunal Analysis. Mixtures of synthetic organic 

compounds (e.g., PCBs and DDT), metals, PAHs, excess 

nutrients, and various inorganic chemicals are released 

into the ocean from municipal and industrial point sources, 

atmospheric deposition, stormwater runoff, spills, and 

groundwater. These anthropogenic contaminants may accumulate in the sediment in coastal bays, estuaries, and 

nearshore coastal zones. 

Two of the most infl uential parameters in the distribution 

of benthic communities are salinity and sediment grain 

size. Environmental concentrations of organic enrichment 

and toxicants are often confounded in space and time with 

gradients of salinity and grain size, making their separate 

and combined biological effects diffi cult to detect, especially at the levels of population and community. However, 

understanding toxic hazard due to sediment contamination 

by means of community assessment is valuable. Biological 

systems integrate the complexity of natural habitat stressors 

and ambient pollutant mixtures, through physical contact 

with sediments, ingestion of sediment, and the bioaccumulation of contaminants via food webs, along with the 

synergetic effects of exposure to multiple toxic chemicals. 

Many examples exist in which marine benthic communities’ response to contaminant and physical stressors have 

been documented (Hartwell and Clafl in, 2005; Hartwell 

and Hameedi, 2007; Hartwell et al., 2009; Oliver et al., 

2011; Wlodarska-Kowalczuk et al., 2005). Impacts of 

contamination on marine benthos have shown that total 

biomass, relative proportion of deposit feeders, and abundance of species with ‘opportunistic’ life histories (e.g. 

high fecundity, short generation time, and rapid dispersal) 

increase with increasing organic enrichment. Some opportunistic taxonomic groups are known to be tolerant of 

chemical toxicants. Others are capable of thriving in physically disturbed habitats (e.g. high sedimentation, dredging 

operations, etc), but not necessarily in contaminated areas. 

In areas impacted by excessive sedimentation from terrestrial runoff, dominant organisms tend toward surface 

suspension feeding modes and high reproductive potential 

regardless of taxonomic relationship, whereas away from 

the sedimentation stress, feeding modes shift to species that 

are deep deposit feeders along with the emergence of fi lter 

feeders. Experimental manipulation of habitats have shown 

that polychaete worms, in specifi c taxonomic lines, with 

opportunistic life history strategies respond positively to organic enrichment (Fleeger et al., 2003). Infaunal arthropods 

respond negatively to toxicants and organic enrichment. 

The response of specifi c arthropod and echinoderm species 

to organic and toxic contamination is mediated by life history and feeding mode characteristics. These observations 

have direct relevance to coral reef condition assessment. 

Finally, the benthic community will respond to management actions that affect physical and chemical stressors in 

vastly shorter time frames than will coral reefs.

Materials and Methods

The sampling strategy for sediments was developed in 

meetings with the STEER Core Planning Group. A stratifi ed random sampling design was selected, which is a 

standard benthic assessment technique. The STEER was 

fi rst subdivided into fi ve strata based on habitat and geography (e.g., hard bottom areas, seagrass beds, mangroves, etc) 

(Figure 3). Five sampling points on soft bottom sediments 

were then randomly selected using ArcGIS®. Both primary 

and alternate sites were identifi ed throughout the STEER. 

Alternate sites were sampled in the event that a primary site 

was unsuitable due to hard bottom, obstructions, etc. 

The stratifi ed random sampling design was used in order 

to characterize the spatial distribution of chemical contaminants, toxicity and the benthic infaunal community 

throughout the STEER. Using this design, the extent and 

concentration of chemical contaminants and bioeffects can 

be compared between strata. The 2011 collection of sediment samples in the STEER occurred 14 - 17 June. The 

samples were collected under DPNR Permit STX-032-11. 

All sediment sites were located using a GPS programmed 

with the site coordinates. Most of the sediment samples 

were collected from the charter vessel Bright Star. Mangrove Lagoon, however, was too shallow for the Bright 

Star. To enable the collection of samples in that stratum, 

personnel from the DPNR Division of Fish and Wildlife 
STEER Sediment Contaminants and Bioeffects Report

Materials and Methods

8

Figure 3. Strata and sediment sites sampled in the St. Th omas East End Reserves (STEER) in June 2011. 
STEER Sediment Contaminants and Bioeffects Report

Materials and Methods

9

brought in a shallow draft motor boat to help NOAA personnel collect the sediment samples in Mangrove Lagoon. 

In addition to the work in 2011, preliminary fi eld work took 

place in May 2010. From that effort, a total of 13 sediment 

samples were taken, and enough funding was available at 

the time to analyze four of the samples collected. The results of the analysis of these samples is also included in this 

report. However, as the four samples were collected from 

targeted sites and were not selected randomly, they could 

not be included in the statistical comparisons between 

strata, nor were they included in the calculation of the mean 

(average) concentration of sediment contaminants in the 

STEER.

Samples for Chemical Contaminant 

Analysis 

The sediments for chemical contaminant analysis were collected using 

standard NOAA National Status and 

Trends (NS&T) protocols (Apeti et 

al., 2012a). The NS&T Program 

within NCCOS monitors the Nation’s 

estuarine and coastal waters for contaminants in bivalve mollusk tissues 

and sediments, and toxicity or bioeffects in sediments. 

Sampling Protocols. A PONAR grab 

(see inset) was deployed to collect the samples using a 

pulley and davit, and retrieved by hand. Rocks and bits of 

seagrass were removed. If a particular grab did not result 

in 200-300 g of sediment, a second grab was made and 

composited with material from the fi rst. If enough sediment had not been collected after three deployments of the 

grab, the site was abandoned and the boat moved on to an 

alternate site. 

A series of protocols (Apeti et al., 2012a) were used to 

avoid contamination of the sediment samples by equipment 

and cross contamination between samples and sites. All 

equipment was rinsed with acetone and then distilled water 

just prior to use at a site. Personnel handling the samples 

also wore disposable nitrile gloves. The top 3 cm of sediment were collected from the grab using a stainless steel 

sediment scoop. This top layer of sediment is referred to 

as surfi cial sediment, and is typically indicative of recent 

deposition. 

Sediments were placed into two certifi ed clean (I-Chem®) 

250 ml labeled jars, one for organic chemical analysis, the 

other for major and trace element analysis, capped and then 

placed on ice in a cooler. Sediments for grain size analysis 

were placed in a WhirlPack® bag, sealed and placed on ice 

in a cooler. At the end of each day, sediment samples for 

contaminant analysis were placed in a freezer. The WhirlPack® bags for the grain size analysis were placed in a 

refrigerator rather than frozen, to avoid altering the grain 

size structure of the sediment.

A series of water parameters (dissolved oxygen, temperature, salinity, and conductivity) were also measured at each 

site, using a YSI® salinity/conductivity/temperature meter. 

The instrument probe was submerged to a depth of approximately 0.5 meter (m) for the surface measurement, and 

within a meter of the sediment for the bottom measurement. 

Secchi depth was also measured at each site. 

 

The sediment samples collected 

were analyzed for a suite of 185 

organic (e.g., hydrocarbons and 

pesticides) and inorganic (e.g., 

metals) contaminants by TDIBrooks International, using protocols established by the NS&T 

Program. The list of chemical 

contaminants analyzed in the sediments is shown in Table 1. The 59 

polycyclic aromatic hydrocarbons 

(PAHs) were analyzed using gas 

chromatography/mass spectrometry in the selected ion monitoring mode. The 37 aliphatic 

hydrocarbons were analyzed by gas chromatography/fl ame 

ionization detection. The 31 organochlorine pesticides and 

38 polychlorinated biphenyls (PCBs) were analyzed using 

gas chromatography/electron capture detection. The four 

butyltins were analyzed using gas chromatography/fl ame 

photometric detection after derivatization. A subset of the 

sediment samples were subsequently reanalyzed using gas 

chromatography/mass spectrometry for confi rmation of 

the TBT concentrations detected at certain sites from the 

initial analysis. The major and trace elements were analyzed using inductively coupled plasma mass spectrometry 

and atomic-fl uorescence spectroscopy. Detailed descriptions of the NS&T protocols, including quality assurance/

quality control (QA/QC) used in the analysis of the organic 

contaminants, can be found in Kimbrough et al. (2006); for 

inorganic analyses, Kimbrough and Lauenstein (2006). 

Statistical Analysis. The sediment contaminant data were 

analyzed using JMP® statistical software. A Shapiro-Wilk 

test was fi rst run on individual parameters to see if the 

data were normally distributed. When data were normally 

distributed, an Analysis of Variance (ANOVA) was run 

followed by pairwise (Tukey HSD) comparisons. If the 

Th e PONAR grab used to take sediment samples in the STEER. 
STEER Sediment Contaminants and Bioeffects Report

Materials and Methods

10

Table 1. Compounds analyzed in sediments from the St. Thomas East End Reserves.

PAHs - Low MW PAHs - High MW Aliphatics Organochlorine Pesticides PCBs Major and Trace ElementsNaphthalene Fluoranthene n-C9 Aldrin PCB8/5 Aluminum (Al)1-Methylnaphthalene Pyrene n-C10 Dieldrin PCB18 Antimony (Sb)2-Methylnaphthalene C1-Fluoranthenes/Pyrenes n-C11 Endrin PCB28 Arsenic (As)2,6-Dimethylnaphthalene C2-Fluoranthenes/Pyrenes n-C12 Heptachlor PCB29 Cadmium (Cd)1,6,7-Trimethylnaphthalene C3-Fluoranthenes/Pyrenes n-C13 Heptachlor-Epoxide PCB31 Calcium (Ca)C1-Naphthalenes Naphthobenzothiophene i-C15 Oxychlordane PCB44 Chromium (Cr)C2-Naphthalenes C1-Naphthobenzothiophenes n-C14 Alpha-Chlordane PCB45 Copper (Cu)C3-Naphthalenes C2-Naphthobenzothiophenes i-C16 Gamma-Chlordane PCB49 Iron (Fe)C4-Naphthalenes C3-Naphthobenzothiophenes n-C15 Trans-Nonachlor PCB52 Lead (Pb)Benzothiophene Benz[a]anthracene n-C16 Cis-Nonachlor PCB56/60 Manganese (Mn)C1-Benzothiophenes Chrysene i-C18 Alpha-HCH PCB66 Mercury (Hg)C2-Benzothiophenes C1-Chrysenes n-C17 Beta-HCH PCB70 Nickel (Ni)C3-Benzothiophenes C2-Chrysenes Pristane Delta-HCH PCB74/61 Selenium (Se)Biphenyl C3-Chrysenes n-C18 Gamma-HCH PCB87/115 Silicon (Si)Acenaphthylene C4-Chrysenes Phytane DDMU PCB95 Silver (Ag)Acenaphthene Benzo[b]fl uoranthene n-C19 2,4'-DDD PCB99 Tin (Sn)

Dibenzofuran Benzo[k]fl uoranthene n-C20 4,4'-DDD PCB101/90 Zinc (Zn

Fluorene Benzo[e]pyrene n-C21 2,4'-DDE PCB105C1-Fluorenes Benzo[a]pyrene n-C22 4,4'-DDE PCB110/77C2-Fluorenes Perylene n-C23 2,4'-DDT PCB118C3-Fluorenes Indeno[1,2,3-c,d]pyrene n-C24 4,4'-DDT PCB128Carbazole Dibenzo[a,h]anthracene n-C25 1,2,3,4-Tetrachlorobenzene PCB138/160Anthracene C1-Dibenzo[a,h]anthracenes n-C26 1,2,4,5-Tetrachlorobenzene PCB146Phenanthrene C2-Dibenzo[a,h]anthracenes n-C27 Hexachlorobenzene PCB149/1231-Methylphenanthrene C3-Dibenzo[a,h]anthracenes n-C28 Pentachloroanisole PCB151C1-Phenanthrene/Anthracenes Benzo[g,h,i]perylene n-C29 Pentachlorobenzene PCB153/132C2-Phenanthrene/Anthracenes n-C30 Endosulfan II PCB156/171/202C3-Phenanthrene/Anthracenes n-C31 Endosulfan I PCB158C4-Phenanthrene/Anthracenes n-C32 Endosulfan Sulfate PCB170/190Dibenzothiophene n-C33 Mirex PCB174C1-Dibenzothiophenes n-C34 Chlorpyrifos PCB180C2-Dibenzothiophenes n-C35 PCB183C3-Dibenzothiophenes n-C36 Butyltins PCB187

n-C37 Monobutyltin PCB194n-C38 Dibutyltin PCB195/208n-C39 Tributyltin PCB201/157/173n-C40 Tetrabutyltin PCB206

PCB209

Abbreviations: MW, molecular weight; PAH, polycyclic aromatic hydrocarbon; HCH, hexachlorocyclohexane; DDMU, 1-chloro-2,2-(p-chlorophenyl)ethylene; DDT, dichlorodiphenyltrichloroethane; DDE, dichlorodiphenyldicloroethylene; PCB, polychlorinated biphenyl
STEER Sediment Contaminants and Bioeffects Report

Materials and Methods

11

data were not normally distributed and a log10 transformation was not effective, Spearman’s nonparametric multivariate correlation was used. Some of the data were also 

subsequently ranked, followed by a Kruskal-Wallis test and 

pairwise comparisons. The statistical analyses were used, 

for example, to compare differences in contaminant levels 

between strata. 

NOAA numerical sediment quality guidelines (SQG) developed by Long and Morgan (1990) and Long et al. (1995), 

known as ERM (Effects Range-Median), and ERL (Effects 

Range-Low), express statistically derived levels of contamination, above which toxic effects would be expected to be 

observed with at least a 50% frequency (ERM), and below 

which effects were rarely (<10 %) expected (ERL). The 

ratio of the ERM value to the sediment concentration for 

each chemical is called the ERM quotient or ERMq (Long 

et al., 1998). The quotient expresses how close measured 

concentrations are to the ERM level on a zero to one scale. 

A quotient of one or greater means the concentrations are 

at or above the ERM. This also normalizes the ERMs for 

different chemicals to a common scale. The mean ERMq of 

all the contaminants averaged together expresses a measure 

of contamination across the entire spectrum of measured 

contaminants. Field research suggests that a mean ERMq 

value of 0.1 is a threshold where degraded communities 

begin to be seen, as observed in the southeast U.S. (Hyland 

et al., 1999). The mean quotient of the ERMs and observed 

contaminant concentrations were calculated on a site by site 

basis. 

Samples for Sediment Toxicity Bioassays

The protocols for the bioassays were based on standard 

methods, as outlined by the U.S. EPA (1999, 2002a) and 

ASTM (2008). Sediment samples for the bioassays were 

collected into three containers. Samples for the amphipod 

toxicity tests (bulk sediment) were collected in 1 liter (L) 

jars; for the sea urchin fertilization tests (porewater extraction), a 3.79 liter (one gallon) sample of sediment was 

collected; and for the P450 test, a sample of sediment was 

taken out of the 250 ml organics jar and extracted. 

Amphipod Toxicity Test. The whole sediment toxicity 

bioassay test is commonly used in North America for assessing sediment quality, in part because the test integrates 

the effects of complex contaminant mixtures in relatively 

unaltered sediment, and also because amphipods are fairly 

common and an ecologically important species in coastal 

waters. The organisms are standard test species with known 

ranges of sensitivity and their presence or absence in a 

particular habitat is not relevant because they are tested 

under standardized conditions. Results of increased mortality, which is signifi cantly different from controls, is considered an indicator of marginal toxicity. Results that are 

signifi cantly different from controls and greater than 20% 

mortality is indicative of highly toxic conditions (Thursby 

et al., 1997). 

Sea Urchin Fertilization Test. The sea urchin (A. punctulata) fertilization toxicity test (also known as the sperm cell 

test) involves exposing sea urchin sperm to sediment pore 

water (interstitial water), followed by the addition of eggs. 

This test is used extensively in assessments of ambient 

water quality, toxicity of industrial and municipal effl uents, 

and sediment toxicity in coastal waters. It combines the 

features of testing sediment pore waters (the phase of sediments in which dissolved toxicants may be bioavailable) 

and exposures of gametes which often are more sensitive 

than adult organisms. Increased fertilization failure which 

is signifi cantly different from controls is considered symptomatic of marginal toxicity. Results that are signifi cantly 

different from controls and greater than 20% below control 

fertilization is indicative of highly toxic conditions (Carr 

and Bidenbach, 1999). 

P450 Test. The HRGS P450 test was used to determine the 

presence of toxic organic compounds in the sediments. Cytochrome P450s are a family of membrane-bound enzymes 

that metabolize a diverse number of compounds, including natural substrates, drugs, hormones, and many toxic 

compounds. They are present in a wide variety of animals, 

plants and other organisms. P450 is shorthand for Pigment 

and 450 is the wavelength at which they most strongly 

absorb light. HRGS stands for Human Reporter Gene System. In this case, a reporter gene is a DNA sequence in a 

human cancer cell line that has been genetically engineered 

to include a gene (the reporter gene) from the fi refl y that 

produces luciferase, the chemical that produces light in the 

insect when presented with the proper substrate. The gene 

is spliced into the region of the DNA strand that is activated to produce P450 enzymes when the cell is exposed 

to chemicals that stimulate metabolic activity. The more 

stimulated the cell is to metabolize a foreign compound, the 

more the reporter gene produces luciferase, which can be 

measured by increased light output. 

Different compounds stimulate P450 production to differing degrees, which can be calibrated. PCBs and PAHs 

stimulate certain Cytochrome P450 enzymes (e.g. CYP1A), 

but each individual compound exhibits its own level of 

stimulation. Heavy metals do not stimulate P450 at all. 

Under appropriate test conditions, induction of CYP1A is 

evidence that the cells have been exposed to one or more 

xenobiotic organic compounds, including dioxins, furans, 
STEER Sediment Contaminants and Bioeffects Report

Materials and Methods

12

planar PCBs, and several PAHs. When run in parallel with 

a serial dilution of standard PAH toxicant benzo[a]pyrene 

(BaP), or TCDD (dioxin), test results can be expressed in 

terms of standard toxicant equivalents based on the relative 

reporter gene response. Samples that exhibited a response 

greater than 50% of a standard 10 nM TCDD threshold 

control were again tested against a B[a]P serial dilution to 

calculate responses normalized to the B[a]P EC50 (effective concentration for 50% of the test cells) or the B[a]P 

equivalents (B[a]P eq). 

Anderson et al. (1999a) calculated the mean and 95% confi dence interval of HRGS values from 527 sampling points 

in the NOAA biological effects database to be 22.7 ±10.1 

(CI=12.6-32.8) mg B[a]P Eq/kg. Hence, values less than 

12.6, forming the tail of the distribution in the direction of 

low induction (or impact) could be interpreted as a minimal 

(background) level. This is consistent with data from pristine sites in Alaska and California where HRGS values did 

not exceed 10.4 mg B[a]P Eq/kg (Anderson et al., 1999b; 

Fairey et al., 1996). Fairey et al. (1996) also demonstrated 

that HRGS values above 60 mg B[a]P Eq/kg were highly 

correlated with degraded benthic communities in San Diego and Mission Bays, and with PAH concentrations above 

the 9,600 μg/kg Probable Effects Level (PEL) guideline 

(MacDonald, 1993), which are similar to the ERLs. Based 

on these data, HRGS values greater than 10 and 60 mg B[a]

P Eq/kg were considered to represent marginal and highly 

contaminated thresholds, respectively.

Differences in the ability of the P450 enzyme system to metabolize chlorinated and non-chlorinated compounds allows 

for differentiation between these classes of compounds in 

environmental samples. Since most PAHs are metabolized, 

they exhibit a maximum response in 6 hours, at which point 

the response begins to fade. Chlorinated hydrocarbons 

(dioxins, furans, and certain PCBs), on the other hand, are 

not degraded and continue to induce CYP1A, resulting in 

increasing responses after 24 hours following exposure. 

Benthic Infaunal Analysis

A benthic community sample was taken with the PONAR 

grab sampler, in addition to the samples for chemical analysis and toxicity testing. The entire contents of an acceptable 

grab (at least 5 cm deep) was sieved on site through a 0.5 

mm mesh. In coarse sediments, nested sieves of 1.0 mm 

and 0.5 mm were sometimes necessary to reduce clogging 

of the screens and damage to the organisms. All organisms were retained in plastic containers and preserved in 

buffered 10% formalin containing Rose Bengal stain and 

sodium borate buffer. 

The following data and information were recorded at each 

site: stratum, site, alternate (if applicable), date, water 

depth, time, latitude, longitude, and depth of sediment in 

the grab. Also included was a written description of each 

sampling site including digital color photographs of the 

site, a physical description of sediment characteristics (texture, color, odor, benthos, sheen) and photographs of the 

undisturbed sediment. 

In the laboratory, all animals were carefully segregated into 

major groups (e.g. worms, clams, shrimp and crabs). They 

were then identifi ed to species unless the specimen was a 

juvenile or damaged. At a minimum, 10% of all samples 

were re-sorted and re-counted on a regular basis. Also, 

10% of samples were randomly selected and re-identifi ed. 

The minimum acceptable sorting and taxonomic effi ciency 

was 95%. A voucher collection composed of representative 

individuals of each species encountered in the project was 

accumulated and retained. 

The benthic communities were characterized by abundance 

(number of animals), number of species, and diversity (a 

type of ratio of abundance and number of species). Abundance was calculated as the total number of individuals per 

grab; species richness as the total number of species represented at a given site; and diversity was calculated with the 

Shannon-Weiner Index (Shannon and Weaver, 1949), using 

the following formula: 

 S

 H’ = -∑ pi (ln pi)

 i=1

where, S = is the number of species in the sample,

i is the ith species in the sample, and 

pi is the number of individuals of the ith species divided by 

the total number of individuals in the sample.

Nonparametric Spearman rank correlation coeffi cients 

were calculated for all parameters to assess relationships 

between the physical, chemical, toxicological and biological variables. Multivariate cluster analysis was employed 

to group site and species data. The objective was to produce 

a coherent pattern of association between sites and species 

(Figure 4). Cluster analysis is a two-step process including: 

1) creation of a resemblance data matrix from the raw data, 

and 2) clustering the resemblance coeffi cients in the matrix. 

The input resemblance (similarity or dissimilarity) matrix 

can be created by a number of methods. Input data may or 

may not be standardized or transformed depending on the 

requirements of the method (e.g. Bray Curtis). Based on 

previous research (Hartwell and Clafl in, 2005), the Jaccard 

method (Goodall, 1973) was used to generate the similarity 
STEER Sediment Contaminants and Bioeffects Report

Materials and Methods

13

matrix. The Jaccard method is 

a binary method based only on 

presence/absence data, and thus 

ignores abundance values. 

Cluster analyses were calculated 

from the matrices using the 

Unweighted Pair-Group Method 

Using Arithmetic Averages (UPGMA) procedure which clusters 

coeffi cients based on arithmetic mean distance calculations 

(Sneath and Sokal, 1973). To 

optimize the cluster analysis 

results, several manipulations of 

the input data were performed 

to remove confounding effects 

and bias:

1- Epibenthic species, such as 

sea anemones and tunicates, 

were eliminated from the 

data set as they are not truly 

infauna.

2- ‘Artifi cial species’ (resulting from failure to identify 

some specimens all the way 

down to species) were identifi ed as a data bias. For example, if specimens of two 

to three species were identifi ed in genus A, and other 

specimens were identifi ed 

only to genus A, this tends 

to artifi cially increase species richness and diversity 

of the sample when in fact 

that diversity is an artifact of 

imperfect taxonomic identifi cation. In some instances, 

specimens were only identifi -

able to family, order or class. 

To address this problem, 

specimens not identifi ed to 

species level were eliminated, 

unless they were identifi ed 

to a taxonomic level below 

which no other specimens in the collection belonged. 

That is, even though they were not identifi ed to species, 

they were the only representative of that taxonomic line 

and did represent a non-redundant taxon. In other cases, 

where a specimen was identifi ed to genus and there was 

only one species identifi ed in that genus, they were combined at the genus level.

3- Rare and unique species were defi ned as those species 

that were found at no more than two sites. Although they 

Figure 4. Combined cluster analysis overlays of species clusters and site clusters. The 

top fi gure illustrates the dominant species communities found in different site clusters. 

The lower fi gure illustrates how different species assemblages distribute themselves 

between different habitats.
STEER Sediment Contaminants and Bioeffects Report

p. 14 14Results and Discussion do contribute to the overall assessment of biodiversity, they 

were eliminated from the cluster analysis data set. Because 

of their limited distribution, by defi nition, they do not 

provide information on the impact of contaminant or other 

stressor gradients in the environment because they do not 

occur across a gradient.

After the data set had been fi nalized, a nodal analysis routine was applied to the data (Lambert and Williams, 1962). 

This consisted of 

combining independent cluster analyses 

in a graphical array. 

The fi rst analysis 

clustered sites using 

species occurrence 

data. The second 

calculation clustered 

species together into 

groups. The intersection of site clusters 

on the abscissa and 

species clusters on the 

ordinate axis yields 

a pattern of species 

associations with 

site clusters, termed 

nodes (Figure 4). In 

practice, this is done 

on large 3ft x 4ft plots 

of the cluster analysis 

output. Reduction to 

normal text page size 

sacrifi ces a signifi -

cant amount of detail. The site and species clusters were 

also characterized by physicochemical habitat parameters, 

contaminant concentrations, and other site-specifi c data. 

Plotting the tabulated values in parallel to the cluster output 

(Figure 5), allows an empirical evaluation of similarities 

in habitat characteristics within and between species and 

site clusters (i.e., what they do or do not have in common) 

to guide interpretation of subsequent statistical contrasts. 

For each species, the parameters were normalized to their 

abundance at each site. 

Once the nodes were defi ned, the species data within each 

node were further assessed with methods developed by 

Clark and Warwick (2001) to assess the relative importance 

of a species in characterizing a set of sites in a quantitative way, called a Similarity Index. Average similarity for a 

species is the contribution of the species to the Bray-Curtis 

similarity within a site group (node). This value indicates 

how typical the species is for the group of sites and ranges 

from 0 to 100%.

Results and Discussion 

Field Data

The collection of 25 sediment samples was planned for 

the June 2011 sampling mission. Twenty-nine sites were 

visited, however, at fi ve sites the fi eld team was unsuccessful in collecting sediments, resulting in sediment samples 

from 24 sites. 

The average water depth at the sites sampled was 7.2 meters (m). As might be expected, the shallower sites were 

in Mangrove Lagoon. The shallowest water depth was 0.6 

m at Site 1-5P in Mangrove Lagoon. The average salinity 

encountered on the surface of the sites was 33.2‰, the average bottom salinity 33.7‰, indicating fairly well mixed 

waters. The highest salinity encountered during the mission 

was 34.6‰, a bottom salinity reading taken at Site 5-61P; 

the lowest salinity encountered (28.3‰) was in Mangrove 

Lagoon on the surface at Site 1-1P. Site specifi c data can 

be found in Appendix A. 

The average water surface temperature at the sites in the 

STEER was 30.1°C, the average bottom temperature was 

29.5°C. A Kruskal-Wallis test run on the ranked data indiFigure 5. Hypothetical representation of the distribution of physicochemical habitat parameters, 

contaminant concentrations, and other site-specifi c data used to characterize site and species 

clusters. 
STEER Sediment Contaminants and Bioeffects Report

p. 15 15Results and Discussion

cated that salinity (p < 0.0001) and temperature (p<0.0001) 

varied signifi cantly by stratum, with lower salinities and 

higher temperatures being found in Strata 1 and 2. 

Total Organic Carbon and Grain Size

The average percent total organic carbon (TOC) in the 

sediments collected was 2.49%, and ranged from a low of 

0.44% to a high of 5.44% 

(Appendix B). A Kruskal-Wallis test run on 

the ranked TOC values 

indicated no differences 

in percent TOC in the 

STEER by stratum (p = 

0.0645). 

Chemical contaminants, 

particularly organic (carbon-containing) contaminants, tend to accumulate 

in sediments with higher 

TOC values. Chemical 

contaminants also tend to 

accumulate in sediments 

that have a higher proportion of the smaller grain 

sizes (i.e., silt and clay). 

Smaller grain size sediments have more surface 

area per unit volume 

available for the adsorption of contaminants, 

and are typically found 

in depositional habitats. 

In addition, metals are 

attracted to sediments 

with higher clay content due to the charge structure on the 

surface of the clay particles. 

For this report, the percent silt and percent clay fractions 

are combined and referred to as percent fi nes (sum of 

percent silt and percent clay sediment fractions). Figure 

6 shows the percent fi nes in the sediments sampled in the 

STEER; the average content was 22.3 ±4.03%. It can be 

seen that areas in Mangrove Lagoon and, to a certain extent 

in Benner Bay, had a higher proportion of percent fi nes in 

the sediments. However, the major sediment size class in 

the STEER was sand (68 ±4.35%). 

Chemical Contaminants

The results from the analysis of each chemical contaminant class are discussed below. More detailed information 

can be found in Appendices C-H. Each of the chemical 

contaminants, along with the bacterial measurement, are 

discussed below.

Polycyclic Aromatic Hydrocarbons. Total PAHs as used 

in this report refers to the sum of the 59 PAH compounds 

and compound classes (e.g., anthracene, C1-napthalenes) 

analyzed in the STEER sediment samples. Appendix C 

contains detailed results of this analysis. A map summarizing total PAHs in the sediments is shown in Figure 7. It can 

be seen that there were a number of higher PAH concentrations, mainly in Mangrove Lagoon and Benner Bay, as opposed to the other strata and sites further offshore. As will 

be seen, the pattern of higher concentrations of chemical 

contaminants in the Mangrove Lagoon and northern Benner 

Bay areas was repeated for a number of the other contaminant classes analyzed.

The mean concentration in the sediment from the STEER 

was 142 ±58 ng/g. The units ng/g (nanogram/gram) are 

also referred to as parts per billion (ppb). The median total 

PAH concentration was 6.02 ng/g. The highest total PAH 

concentration was at site 1-3P, with 1,131 ng/g. In ManFigure 6. Percent fi nes (percent silt plus percent clay fractions) in sediments from the 

STEER. 
STEER Sediment Contaminants and Bioeffects Report

p. 16 16Results and Discussiongrove Lagoon, the mean concentration of total PAHs in 

the sediments was 425 ±214 ng/g, with the standard error 

indicating a wide range in the concentrations in this stratum 

(Stratum 1). The lowest concentration of total PAHs was 

found in Stratum 4, at site 4-49P (0.93 ng/g) near St. James 

Island. From the preliminary sampling for this project in 

2010, the highest concentration of total PAHs was found at 

the ML-10 site in Mangrove Lagoon, at 951 ng/g (Appendix C). 

Variation of Total PAHs 

Across Strata. A Kruskal-Wallis test run on the 

ranked data indicated a 

signifi cant difference in 

total PAHs by stratum 

(p = 0.0210). A Tukey’s 

HSD (Highly Signifi -

cant Difference) analysis indicated that only 

Stratum 1 and Stratum 

4 were signifi cantly different, due in part to the 

large standard errors in 

total PAHs within each 

stratum. Note that the 

targeted samples collected in 2010 were not 

included in the statistical 

analysis by stratum. 

Comparison with Other 

Data. EPA’s Environmental Monitoring and 

Assessment Program 

(EMAP) was developed 

to monitor and assess 

the status and trends in national ecological resources (EPA, 

2000). In 2004, sediment samples were collected and analyzed by EMAP at a number of locations around St. Thomas. Four of those sites were in the STEER; two sites were in 

Benner Bay, and one site each in Jersey Bay and Great Bay. 

The four EMAP sites are also included in Figure 3. A suite 

of 23 PAHs were analyzed in the sediments at each site. 

The detection limit for each PAH analyzed by EMAP was 

10 ng/g. None of the sediments sampled within the STEER 

boundaries by EPA’s EMAP had a detectable level of the 

PAHs analyzed. 

Recent chemical contaminant studies have also been 

conducted in Puerto Rico and can be used to compare with 

the results found in the STEER. In Vieques, Puerto Rico, 

the mean concentration of total PAHs was 52.3 ±8.7 ng/g, 

somewhat below total PAHs found in the STEER sediments 

(Pait et al., 2010). In southwest Puerto Rico, Pait et al. 

(2008) reported a mean total PAH concentration in the sediments of 80.6 ±25.5 ng/g, also lower than the mean found 

in the STEER. 

Because of the national-level contaminant monitoring carried out by NOAA’s NS&T Program, data from the STEER 

can be compared with data from the rest of the Nation’s 

coastal waters. For this report, data from the STEER 

sediments are compared with the most recent (2006/2007) 

nationwide analysis of sediments from the NS&T Program. 

The most recent NS&T nationwide sediment analysis data 

were used, as the individual compounds in some of the 

chemical contaminant classes (e.g., total PAHs, total PCBs 

and total DDT) that NS&T analyzes, have changed over 

time, and the 2006/2007 NS&T sediment data contains the 

most comparable list of analytes. 

The NS&T 2006/2007 median (NS&T median) for total PAHs is 395 ng/g. Three sites, two of which were in 

Mangrove Lagoon (1-3P, 1-2P, and 3-32P), were above the 

NS&T median for total PAHs. None of the sites sampled in 

Figure 7. Total polycyclic aromatic hydrocarbons (PAHs) detected in sediments from the St. 

Thomas East End Reserves.
STEER Sediment Contaminants and Bioeffects Report

p. 17 17Results and Discussion

the STEER approached the NS&T 2006/2007 85th percentile (NS&T 85th percentile) of 2,883 ng/g. The median 

(i.e., the “middle value”) and 85th percentile values (elevated contaminant concentrations), are used to show how the 

results from the STEER sediments compare with NOAA’s 

national results.

NOAA Sediment Quality Guidelines for Total PAHs. As 

noted earlier, the NS&T Program developed effects-based, 

numeric guidelines to estimate the toxicological relevance 

of certain sediment chemical contaminants (Long et al., 

1998). These guidelines, the Effects Range-Low (ERL) 

and the Effects Range-Median (ERM) defi ne sediment 

contaminant concentration ranges that are rarely (<ERL), 

occasionally (ERL to ERM) or frequently (>ERM) associated with toxic effects in aquatic biota (NOAA, 1998). The 

ERL and ERM values for total PAHs are also shown in 

Figure 7. As can be seen, total PAHs in the sediments were 

below the ERM and ERL as well. 

NOAA’s NS&T Program has developed ERL and ERM 

guidelines for a number of individual PAHs, which are 

shown in Table 2. None of the sediments collected in 

the STEER exceeded the ERL, ERM or the NS&T 85th 

percentile for any of the individual PAHs listed in Table 2. 

However, from the 2011 stratifi ed random sampling, Sites 

1-2P, 1-3P and 3-32 exceeded the NS&T median for a number of the individual PAHs listed (Table 2). From the 2010 

targeted sampling, BB-1, BB-2 and ML-10 also exceeded 

the median for a number of the listed PAHs. As will be 

seen later, results from the P450 test indicated a response to 

PAHs in Mangrove Lagoon and northern Benner Bay. 

The ratios of phenanthrene-to-anthracene (P/A) and 

fl uoranthene-to-pyrene (F/P) have been used as a screening tool to assess the relative contributions of pyrogenic 

(combustion-related) versus petrogenic (uncombusted) 

sources of PAHs (Budzinski et al., 1997). Higher levels 

of uncombusted PAHs would be more indicative of the 

presence of spilled fuels, such as gasoline or oil. P/A ratios 

less than 10 are more indicative of pyrogenic sources; F/P 

ratios greater than 1 are also thought to be associated with 

pyrogenic sources. Most of the sites in the STEER had P/A 

ratios of less than 10, and the F/P ratio close to or above 

1, indicating the pyrogenic nature of the PAHs present in 

the sediments. At 1-3P in Mangrove Lagoon, which had 

the highest total PAH level in the samples analyzed from 

the STEER, the P/A ratio was 3.24, indicating pyrogenic 

sources, however the F/P ratio was 0.70, indicating that 

petrogenic sources may also have contributed to the mix of 

PAHs found in the sediments at this site. 

Effects of Sediment Grain Size and TOC. As noted earlier, 

the adsorption of organic contaminants onto sediments is 

strongly infl uenced by grain size (Hassett et al., 1980). The 

smaller grain sizes of the silts and clays have proportionally higher surface areas available for the adsorption of 

chemical contaminants and tend to have more TOC than 

coarse grained sediment. To assess this relationship for the 

samples collected in the STEER, a nonparametric regression was run between percent fi nes (sum of percent silt and 

percent clay) and the concentration of total PAHs found 

in the sediment samples. There was a highly signifi cant 

(P < 0.0001) and positive correlation between the percent 

fi nes and the concentration of total PAHs. There was also 

a signifi cant negative correlation (p <0.0001) between the 

concentration of PAHs and the sand fraction of the sediments, indicating that as the percent sand concentration increased in sediments, the amount of total PAHs present was 

correspondingly lower. A regression run between percent 

gravel in the sediments and total PAHs was not signifi cant 

(p = 0.4065). 

Typically, a positive relationship also exists between sediment total organic carbon (TOC) and chemical contaminants in freshwater, estuarine and coastal waters (Shine 

and Wallace, 2000; Hassett et al., 1980). Because of this, 

organic contaminant concentrations are often normalized 

to the organic carbon content of sediments. However, a 

Table 2. Comparison of higher concentrations of individual PAHs at STEER sites with NOAA NS&T data.

Sites NS&T Statistics and Guidelines

Compound 1-2P 1-3P 3-32P BB-1 BB-2 ML-10 Median 85th Percentile ERL ERM

Acenaphthylene 2.2 3.4 0.2 2.8 4.0 2.4 2.1 15.1 44 640

Anthracene 3.2 5.6 1.3 7.4 9.2 5.7 3.4 38.7 85.3 1,100

Napthalene 7.3 9.2 0.9 5.4 6.4 7.3 3.7 27.6 160 2,100

Benzo-a-pyrene 20.3 35.0 35.1 9.6 17.5 15.6 14.7 127 430 1,600

Dibenzo(a,h)anthracene 3.4 6.4 8.2 7.4 6.9 11.6 5.0 23.8 63.4 260

All concentrations are in ng/g.
STEER Sediment Contaminants and Bioeffects Report

p. 18 18Results and Discussionnonparametric correlation between TOC 

and total PAHs for 

the STEER samples 

was not signifi cant 

(Spearman Rho = 

-0.1779, p = 0.4057).

 

Interestingly, TOC 

also showed no 

signifi cant correlation with either 

the silt (Spearman 

Rho = -0.2435, p = 

0.2515), clay (Spearman Rho = -0.1331, 

p = 0.5353) or fi nes 

(Spearman Rho = 

-0.2531, p = 0.2328) 

fractions of the 

sediment. TOC is 

typically associated 

with the smaller size 

fractions, particularly 

the silts. It is unclear 

why a signifi cant 

relationship between 

TOC and grain size 

also did not exist for 

the sediments in STEER. Perhaps the organic carbon in 

these sediments is in a different form or is cycled differently than in estuarine and/or temperate areas. It was noted 

earlier that while a number of the inshore sites had elevated 

TOC levels, some of the more offshore sites (e.g., 4-46P, 

3-37A, 4-49P, and 4-47P) also had higher TOC levels (Appendix B). The grain size distribution in these more offshore areas, however, was primarily sand and gravel. 

Work in Vieques and Jobos Bay, Puerto Rico indicated a 

strong relationship between PAHs and TOC (Pait et al., 

2012; Pait et al., 2010). However, work in southwest 

Puerto Rico indicated results similar to the STEER, that is 

no relationship between TOC and PAHs in the sediment 

(Pait et al., 2008). Additional work is needed to assess the 

relationship between grain size and TOC in the sediments 

in STEER and possibly in other tropical areas.

Total Extractable Hydrocarbons. The results of the analysis of total extractable hydrocarbons, or TEH, is shown in 

Figure 8. TEH is not only composed of PAHs, such as those 

occurring from the combustion of fuels, but also of straight 

and branched aliphatics (nonaromatic hydrocarbons) found 

in uncombusted fuels and in oils, and from natural sources 

(e.g., decaying vegetation). TEH provides a more complete 

assessment of the total mass of hydrocarbons present in a 

sediment sample. 

It can be seen from Figure 8 that the relative concentration of TEH in the STEER mirrors total PAHs (Figure 7). 

It should be noted, however, that the units for total PAHs 

are in ng/g (ppb), while TEH is in μg/g (ppm or parts per 

million). TEH in the sediments at a number of locations 

in the STEER were approximately an order of magnitude 

higher than total PAHs. The mean TEH concentration in 

the STEER was 167 μg/g. The highest TEH concentration 

(1,104 μg/g) was found in Mangrove Lagoon at 1-3P. 

Variation of TEH Across Strata. An ANOVA run on the 

log10 transformed data indicated that TEH varied by stratum (p = 0.0018), and a Tukey-Kramer HSD test indicated 

that Stratum 1 was signifi cantly different (higher) than 

Strata 3, 4 and 5. 

Sediment Quality Guidelines and TEH. There are no 

NOAA sediment quality guidelines for TEH. Boehm et 

al. (2008) carried out a regression analysis between total 

Figure 8. Total extractable hydrocarbons (TEH) detected in sediments from the St. Thomas East 

End Reserves.
STEER Sediment Contaminants and Bioeffects Report

p. 19 19Results and Discussion

PAHs and TEH, 

and calculated a 

TEH “ERL” of 

2,600 μg/g, and a 

TEH “ERM” of 

9,760 μg/g. Using these values 

as rough TEH 

sediment quality 

guidelines, none 

of the TEH concentrations found 

in the STEER 

exceeded the lower 

threshold estimated 

by Boehm et al. 

(2008). 

Effects of Sediment Grain Size 

and TOC. A nonparametric correlation run between TEH 

and percent fi nes indicated a signifi cant positive correlation 

(Spearman Rho = 0.5852, p = 0.0027), however, there was 

no signifi cant correlation between TEH and TOC (Spearman Rho = -0.0030, p = 0.9887). 

Aliphatics. In addition 

to TEH, straight chain 

and branched aliphatics, indicative of uncombusted fuels or oil, 

were also analyzed in 

the sediment samples 

(Figure 9). There were 

a number of aliphatics 

in the C-19 (molecules 

containing 19 carbons), 

and the C-23 - C-31 

range, with spikes at 

C-19 and C-27, particularly at Site 3-32P 

but also at Site 5-70A. 

The aliphatics present appear to be in the 

range of diesel fuel and 

lubricating oils (Libes, 

1992), and could 

indicate some type of 

discharge in the past 

or perhaps low level, 

chronic (longer term) 

inputs at this site. 

Polychlorinated Biphenyls. Total PCBs detected in the 

sediments are shown in Figure 10. Appendix E contains 

results of the analysis for individual PCBs. Total PCBs as 

included in this report represents the sum of the 38 congeners analyzed for the project. 

Figure 10. Total PCBs detected in sediments from the St. Thomas East End Reserves.

Figure 9. Straight chain and branched hydrocarbons (aliphatics) in sediments from the St. Thomas East End Reserves.
STEER Sediment Contaminants and Bioeffects Report

p. 20 20Results and Discussion The mean concentration of total PCBs found in the STEER 

was 1.00 ±0.32 ng/g; the median was 0.37 ng/g. As with 

the PAHs, there was a pattern of somewhat elevated levels 

of total PCBs in Mangrove Lagoon and in the northern 

Benner Bay areas. 

The highest concentration of total PCBs from the stratifi ed random sampling was 7.2 ng/g; from the targeted 2010 

sampling, the highest concentration was 65.9 ng/g at BB-2 

(Figure 10). Eighteen, or 75%, of the sites sampled in the 

STEER, however, had a total PCBs concentration of less 

than 1 ng/g. 

Variation of Total PCBs Across Strata. The variation of 

total PCBs by stratum was assessed using an ANOVA, run 

on the log10 normalized concentration values. The results 

indicated no signifi cant variation (p = 0.0573) in total PCBs 

concentration across the fi ve 

strata established in the STEER.

Comparison with Other Data.

EPA’s EMAP sampled and 

analyzed sediments in the 

STEER from four locations in 

2004 (Figure 3). A total of 21 

congeners were analyzed in the 

sediment samples taken. No 

PCB congeners were detected in 

the four samples analyzed; the 

detection limit for each congener was 0.05 ng/g.

In a project conducted by 

NCCOS in Jobos Bay, the mean 

total PCBs concentration found 

in the sediments was 2.09 ±0.50 

ng/g (Pait et al., 2012). In Vieques, that value was 2.86 

±0.14 ng/g, both higher than the STEER. In southwest 

Puerto Rico, the mean total PCBs concentration in sediments was 12.1 ±2.26 ng/g not including two very high total PCBs concentrations (1,022 ng/g and 2,710 ng/g) within 

Guanica Bay. If the two sites in Guanica Bay are included, 

the mean for total PCBs in the southwest Puerto Rico study 

area was 74.7 ±47.9 ng/g (Pait et al., 2008). 

Four of the fi ve sites from the stratifi ed random sampling 

(in Mangrove Lagoon and northern Benner Bay) had a total 

PCBs concentration above the NS&T median of 2.2 ng/g. 

All four of the 2010 targeted sample were above the NS&T 

median. BB-2 (65.9 ng/g) from the targeted sampling was 

above the 85th percentile (23.7 ng/g) for total PCBs. 

NOAA Sediment Quality Guidelines for Total PCBs. ERLs 

and ERMs have been established for total PCBs. The concentration of total PCBs at Site BB-2 (65.9 ng/g) from the 

targeted sampling was higher than the PCB ERL (Figure 

10). At 21.8 ng/g, ML-10 was just below the ERL. Levels 

below the ERL indicate that effects on benthic infauna are 

not as likely. Concentrations above the ERL but below the 

ERM indicate that more sensitive species or life stages may 

begin to be impacted. 

Effects of Grain Size and TOC. A nonparametric analysis of the data revealed a signifi cant positive correlation 

between total PCBs and the fi nes fractions of the sediment 

(Spearman Rho = 0.5452, p = 0.0059). No signifi cant correlation existed between total PCBs and gravel, and there 

was a signifi cant negative correlation (Spearman Rho = 

-0.4648, p = 0.014) between sand and total PCBs. 

An analysis of total PCBs 

and TOC revealed no 

signifi cant correlation 

(Spearman Rho = 0.0322, p 

= 0.8813), similar to what 

was observed for PAHs. 

For both PAHs and PCBs 

in the STEER, sediment 

concentrations appeared 

to be infl uenced more by 

sediment particle size than 

sediment TOC. 

DDT and Other Organochlorine Pesticides. Figure 

11 contains the results of 

the analyses of total DDT 

in sediment samples from 

the STEER. Detailed results for DDT and a number of other organochlorine pesticides analyzed for this project can be 

found in Appendix F. Total DDT as defi ned in this report 

is the sum of the parent isomers (4,4’-DDT and 2,4’-DDT), 

along with degradation products DDE, DDD and DDMU. 

The mean concentration of total DDT in the sediments in 

the STEER was 0.047 ±0.025 ng/g; the median was 0.002 

ng/g. As with a number of the other chemical contaminants, higher concentrations of total DDT were found in 

the Benner Bay and Mangrove Lagoon areas. The highest 

total DDT concentration from the stratifi ed random samples 

collected in 2011 was 0.609 ng/g at 2-20P (Table 3). The 

highest concentration of total DDT from the 2010 targeted 

sampling was 3.61 ng/g at BB-2 (Figure 3) in northern 

Benner Bay. The second highest concentration was also 

in Benner Bay (1.31 ng/g) at BB-1. Currently, there does 

A

a

s

(

=

w

F

i

c

t

s

s

D

c

Sampling of sediments in the STEER.
STEER Sediment Contaminants and Bioeffects Report

p. 21 21Results and Discussion

Figure 11. Total DDT detected in sediments from the St. Thomas East End Reserves.

not appear to be much 

agriculture on the island 

of St. Thomas, although 

in the past DDT could 

have been used on crops 

such as sugarcane, fruits 

and vegetables, along 

with use to control mosquitoes. 

Variation of Total 

DDT Across Strata. 

Although there were 

some elevated levels 

of DDT in Benner Bay 

and Mangrove Lagoon 

(Table 3), an ANOVA 

run on log10 normalized data indicated no 

signifi cant variation (p 

= 0.2575) in total DDT 

concentration across 

the fi ve strata in the 

STEER. In addition, 

the degradation products DDD and DDE 

appeared to make up 

much of the total DDT 

present, indicating that the parent compound had degraded 

over time. 

Comparison with Other Data. EPA’s EMAP analyzed DDT 

along with a number of DDT degradation products from 

four sites in the STEER. The only DDT-related compound 

detected was the degradation product 4,4’-DDD, at a 

concentration of 0.26 ng/g at one site. In southwest Puerto 

Rico, Pait et al. (2008) detected a mean total DDT concentration of 2.10 ±1.26 ng/g, higher than in the STEER. In 

Jobos Bay, the mean total DDT concentration was 0.54 

±0.10 ng/g. In Vieques, the mean concentration of total 

DDT in the sediments was substantially higher, 23.6 ±16.5 

ng/g, due in 

part to elevated 

concentrations 

at four (78 ng/g 

to 1,274 ng/g 

total DDT) sediment sampling 

sites (Pait et al., 

2010). 

The concentration of total DDT in the STEER exceeded 

the NS&T median value of 0.395 ng/g at four sites in the 

STEER, three of those from the 2010 targeted sampling. 

(Table 3). The concentration of total DDT at BB-2 was just 

above the NS&T 85th percentile of 3.49 ng/g.

NOAA Sediment Quality Guidelines for Total DDT. The 

concentration of total DDT at BB-2 (3.61 ng/g) from the 

2010 targeted sampling was also above the ERL (1.58 

ng/g). However, none of the sites sampled in the STEER 

had a concentration above the DDT ERM.

Effects of Sediment Grain Size and TOC. A nonparametric analysis of the data revealed no signifi cant correlation 

Sites NS&T Statistics and Guidelines

Compound 1-5P 2-16P 2-20P BB-1 BB-2 ML-10 Median 85th Percentile ERL ERM

Total DDT 0.10 0.082 0.609 1.31 3.61 0.86 0.395 3.49 1.58 46.1

Chlordane 0.07 0.18 0.02 0.22 0.2 0.85 0.195 0.975 0.5 6

Total Endosulfan 0.0 0.0 0.142 0.0 1.13 0.63 0.0 0.253 N/A N/A

Chlorpyrifos 0.0 0.253 0.0 1.33 0.13 0.62 0.01 0.328 N/A N/A

N/A, not available

Table 3. Comparison of higher concentrations of pesticides at STEER sites with NOAA NS&T data.
STEER Sediment Contaminants and Bioeffects Report

p. 22 22Results and Discussionbetween total DDT and percent fi nes (Spearman Rho = 

0.2993, p = 0.1554), or total DDT and percent TOC (Spearman Rho = -0.0060, p = 0.9776), however, it should be 

noted that 13 of the 24 stratifi ed random samples had no 

detectable level of total DDT. 

Additional Pesticides. A number of other pesticides were 

analyzed in the sediments from the STEER as part of this 

project. Most of the results were below detection limits. 

Selected results are shown in Table 3; the rest can be found 

in Appendix F. The highest concentration of chlordane (alpha and gamma isomers) detected in STEER sediments was 

0.85 ng/g at site ML-10 at the mouth of Turpentine Gut, 

which empties into Mangrove Lagoon. This concentration 

is above the NS&T median but below the NS&T 85th percentile for chlordane (Table 3). NOAA has also established 

ERL and ERM values for chlordane. Chlordane was above 

the ERL only at ML-10. None of the sites had a chlordane 

concentration above the ERM. 

The insecticides endosulfan 

and chlorpyrifos have had both 

agricultural and nonagricultural 

(e.g., homeowner) uses. Endosulfan, an organochlorine 

insecticide, is currently being 

phased out for all uses due to 

health risks to farmworkers and 

wildlife, and its persistence in 

the environment (EPA, 2010). 

Since there appears to be little 

commercial agriculture currently 

on St. Thomas, it is likely that 

endosulfan was used in the past, 

perhaps also on vegetables and 

fruits in gardens, prior to being 

phased out for homeowner use. The highest concentration of total endosulfan (sum of endosulfan I and II and 

endosulfan sulfate) detected in the STEER (1.13 ng/g) was 

at BB-2 in Benner Bay, which is above the NS&T median 

and 85th percentile. There are no NOAA sediment quality 

guidelines for endosulfan. 

Although the organophosphate insecticide chlorpyrifos has 

had widespread use both domestically and in agriculture, 

virtually all homeowner uses have been eliminated (EPA, 

2002b). Chlorpyrifos can still be used on certain food 

crops, on golf courses, for wood treatment (nonstructural), 

and as an adult mosquitocide. The highest concentration of 

chlorpyrifos (1.33 ng/g) was in Benner Bay at BB-1. This 

concentration was above the NS&T median and also above 

the 85th percentile (Table 3). The concentration of chlorpyrifos at ML-10 was also above the NS&T median and 85th 

percentile. There are no NOAA sediment quality guidelines for chlorpyrifos in sediments. 

Tributyltin (TBT). The results of the analysis of butyltins 

in STEER sediments are shown in Figure 12 and in Appendix G. Mono-, di-, tri-, and tetrabutyltins were analyzed in 

the sediments. Tetrabutyltin is an intermediate in the manufacture of TBT compounds. As noted earlier, TBT has had 

extensive use in the past as an antifoulant on boat hulls. In 

the environment, TBT degrades to dibutyltin, then monobutyltin, and fi nally to inorganic tin. Experiments have shown 

that the half-life of TBT, the amount of time needed to convert half of the TBT to dibutyltin in natural water samples, 

is on the order of days; degradation to monobutyltin takes 

approximately a month (Batley, 1996). Experiments with 

aerobic sediments have shown that the half-life of TBT is 

similar to that measured in solution. In deeper, anoxic sediments, however, the half life of TBT appears to be considerably longer, on the order of 2-4 years (Batley, 1996). 

The mean, or average, 

concentration of TBT in the 

sediments in the STEER 

was 1.85 ±1.30 ng Sn/g; the 

median was zero. The highest concentration of TBT detected in STEER sediments 

collected using the stratifi ed 

random sampling design was 

at site 2-20P in Benner Bay, 

with a concentration of 31 

ng/g. 

However, of the samples 

analyzed from 2010, BB-1 

and BB-2 had even higher 

TBT concentrations. The concentration of TBT at BB-1 

was 77 ng/g; the TBT concentration at BB-2 was even 

higher, 248 ng/g. 

Variation of TBT Across Strata. Because the targeted 2010 

samples were collected nonrandomly, that data cannot be 

used to assess the variation of TBT in sediments across the 

STEER strata. An ANOVA run on the log10 transformed 

data for the 2011 samples collected using the stratifi ed random design did not indicate any signifi cant differences (p = 

0.4368) in the concentration of TBT between strata. 

Comparison with Other Data. The NS&T median concentration of TBT in sediments is 0.16 ng Sn/g. The NS&T 

85th percentile for TBT is 1.38 ng Sn/g, which is lower 

than the mean concentration of TBT found in STEER sediments. The highest concentration of TBT detected in the 

T

c

s

w

m

e

t

c

r

a

w

n

H

Sediment sample in the PONAR grab from Stratum 1 (Mangrove Lagoon). 
STEER Sediment Contaminants and Bioeffects Report

p. 23 23Results and Discussion

Figure 12. Tributyltin detected in sediments from the St. Thomas East End Reserves. BB-1 and BB-2 

represent targeted, nonrandomized samples taken in 2010. 

STEER (248 ng Sn/g) represents the third highest detection 

ever in sediments in NOAA’s NS&T Program (not just the 

2006/2007 nationwide sediment sampling). The only two 

higher TBT concentrations from NOAA’s NS&T Program 

were from the Elizabeth River in the southern Chesapeake 

Bay area, and Elliot Bay in Puget Sound. Pait et al. (2008) 

detected a mean TBT concentration of 0.01 ±0.01 ng Sn/g 

in southwest 

Puerto Rico. 

In Vieques, 

Puerto Rico, 

the mean 

concentration 

of TBT was 

0.05 ±0.02 

ng Sn/g and 

in Jobos Bay, 

the mean 

concentration was 0.56 

±0.28 ng 

Sn/g. 

It should 

be noted, 

however, 

that 15 of the 

24 sediment 

samples 

taken in the 

STEER had 

no detectable 

TBT. The 

higher concentrations of 

TBT tended 

to occur in 

the northern 

Benner Bay 

area. For the most part, this was also the case for the TBT 

degradation products dibutyltin and monobutyltin (Appendix G). 

Sediment Quality Guidelines and TBT. There are no established sediment quality guidelines for TBT, due in part 

to the complex chemistry of this compound, including its 

bioavailability largely being governed by partitioning into 

porewater (water in between sediment particles), which is 

in turn is governed by a number of parameters of the sediment at a site. 

One of the few attempts at establishing guidelines for TBT 

was reported by Weston (1996). In that document, lower 

and upper screening values were established for TBT, based 

on a sediment organic carbon content of 2%. The intent 

was to establish thresholds for cleanup actions at contaminated sites. The lower and upper values are not analogous 

to NOAA ERL or ERM values, but rather represent a range 

that was to be used to determine when additional testing 

(e.g., additional toxicity testing) at a site would be advisable. Using this approach, Weston (1996) recommended 

TBT values between 10 and 144 ng Sn/g as the lower 

and upper screening values, respectively, with the actual 

screening value selected being determined by an EPA site 

manager at the particular EPA Superfund site. If these two 

values are used as rough boundaries for determining when 

additional work (e.g., toxicity testing) would be recommended, it indicates there should be concern regarding the 

elevated TBT level at BB-2, especially as the concentration 

was above the higher screening value developed by Weston 

(1996). Sites BB-1 and 2-20P were above the lower 

screening value but below the upper screening value, but 

are also of concern. The results did not change even when 

the organic carbon content from each of these three sites 
STEER Sediment Contaminants and Bioeffects Report

p. 24 24Results and Discussion

was incorporated into the equations used in Weston (1996), 

including BB-2, which had an organic carbon content of 

roughly 2% (Appendix B). 

Butyltin Levels in the Sediments Northern Benner Bay. 

A comparison was made with butyltin data generated in 

northern Benner Bay and by NOAA/NCCOS in Puerto 

Rico. A summary of the results for TBT and its metabolites 

in southwest Puerto Rico (Pait et al., 2007) and Vieques, 

Puerto Rico (Pait et al., 2010) is shown in Figure 13. From 

this fi gure, it can be seen that the majority of the butyltin 

present in the sediment samples from southwest Puerto 

Rico, and in Vieques, were primarily in the form of monobutyltin and dibutyltin, with only a small fraction of the 

total as the parent or undegraded TBT. 

Figure 14 shows the same type of information for the three 

sites in the STEER that had the highest TBT concentrations. Not only are the absolute concentrations vastly 

different, the ratios of TBT to monobutyltin and dibutyltin 

at these three sites are different from those shown in Figure 

13. The concentration of TBT at these three sites in the 

STEER was similar to, if not higher than, the concentration 

of monobutyltin and dibutyltin at these same sites. The 

higher concentrations of TBT relative to monobutyltin and 

dibutyltin, along with the overall higher concentration of 

TBT, may be indicative of recent deposition of TBT. For 

example, as a result of the mooring of boats and/or the 

cleaning and scraping of boat bottoms containing TBTbased paints, with subsequent input of these materials (e.g., 

Mean butyltins in sediments from southwest Puerto Rico.

% indicates percent of butyltin total

Mean butyltins in sediments from Vieques, Puerto Rico.

Figure 13. Tributyltin detected in sediments from southwest Puerto Rico and Vieques, Puerto Rico. Values represent means. 

Mean butyltins in sediments from 20P in the STEER (2011).

% indicates percent of butyltin total

Figure 14. Tributyltin detected in sediments from three 

sites in the STEER. 

Mean butyltins in sediments from BB-1 in the STEER (2010).

Mean butyltins in sediments from BB-2 in the STEER (2010).
STEER Sediment Contaminants and Bioeffects Report

p. 25 25Results and Discussion

paint chips or dust) through stormwater runoff into adjacent 

waters. 

The higher levels of TBT found could also be related to 

past deposition. As noted, the sediment samples analyzed 

as part of this project were surfi cial or surface sediments. 

For the analysis, the top three cm (centimeters) of sediment were collected from the sediment grab. Given this, it 

is likely that the samples analyzed in the STEER represent 

more recently deposited sediments. However, in order to 

confi rm this, additional studies would be useful to assess 

the sedimentation rate in this part of Benner Bay, along 

with data from sediment cores to track concentrations back 

in time. As part of the monthly monitoring in the STEER 

being conducted by UVI, six sediment traps have been 

installed in the STEER which include sites in Mangrove 

Lagoon, Benner Bay, Rotto Cay, Cowpet Bay, and adjacent 

to Great St. James and Little St. James. Preliminary results 

(January - May 2012) indicate terrestrial inputs are signifi -

cant at all sites, and that deposition rates in the sediment 

traps using these preliminary data appear higher at the Benner Bay and Rotto Cay locations. 

Regardless of whether the TBT found in the Benner Bay 

area is from past inputs, more recent input, or both, the 

elevated levels suggests the need for additional work to 

quantify the distribution of this contaminant in the sediments along with effects (toxicity), including possible 

endocrine disruption in mollusks. As noted earlier, Strand 

et al. (2009) found evidence of elevated levels of TBT and 

its degradation products in several gastropod species, as 

well as imposex at several locations, including Charlotte 

Amalie Bay in St. Thomas. As part of the current project in 

the STEER, samples of queen conch (Strombus gigas) and 

coral (Porites astreoides) are being analyzed for chemical 

contaminants, including butyltins, and will be reported in a 

later publication. 

At the very least, additional work is needed to further quantify the lateral and vertical (i.e., sediment cores) distribution 

of TBT in the sediments in the northern part of Benner Bay. 

Analyzing the concentration of TBT and its metabolites 

in sediment cores would provide a better understanding of 

degradation rates and concentrations of TBT in sediments 

over time, along with the total amount of TBT that may be 

present in the area. This would be particularly important if 

construction or dredging operations in this part of Benner 

Bay were to occur in the future, so as to limit the transport 

and impact of contaminated sediments. As will be seen, 

copper was also elevated in this part of the STEER with 

the highest copper sediment concentration, like the highest TBT concentration, occurring at BB-2. Copper is an 

important component of current and past antifouling paint 

formulations. 

Effects of Sediment Grain Size and TOC. The correlation 

of TBT concentrations to grain size and TOC was examined for sediments sampled in the STEER. A nonparametric analysis of the data revealed a signifi cant correlation 

between TBT and percent fi nes (Spearman Rho = 0.5759, 

p = 0.0032). As noted earlier, smaller grain sizes (silt and 

clays) of sediments have more surface area available for 

the adsorption of contaminants. There was no correlation, 

however, found between TBT and percent TOC (Spearman 

Rho = 0.0430, p = 0.8419), similar to what was seen for a 

number of the other organic chemical contaminants analyzed for this project. 

Cadmium. Seventeen major and trace elements were analyzed in the sediment samples collected. Detailed results 

for all of these elements are contained in Appendix H. The 

discussion that follows focuses on those trace elements that 

have been shown to be toxic at low concentrations, and 

for a number of these elements that were found at elevated 

concentrations in the STEER sediment. 

The concentration of cadmium in the sediments sampled in 

the STEER can be seen in Figure 15. The mean concentration in the STEER sediments was 0.03 ±0.02 μg/g. Only 

three sediment samples from the stratifi ed random sampling 

had a detectable level of cadmium, including 1-1P and 

1-3P in Mangrove Lagoon, and 2-16P in Benner Bay. The 

highest concentration of cadmium in these samples was 

0.264 μg/g at site 1-3P. Of the four samples collected in 

2010, the highest concentration was 0.371 μg/g at ML-2 in 

Mangrove Lagoon (Appendix H). At BB-2, no cadmium 

was detected. 

Variation of Cadmium Across Strata. Because of the low 

number of detections of cadmium in the STEER, no analysis by stratum was carried out. 

Comparison with Other Data. EPA’s EMAP analyzed 

cadmium in sediments from four locations in the STEER. 

The mean concentration of cadmium was 0.25 μg/g, higher 

than the mean detected in the STEER in the current project. 

In southwest Puerto Rico, the mean cadmium concentration in sediments was 0.01 μg/g, similar to that found in the 

STEER. In Vieques, the mean cadmium concentration in 

sediments was 0.13 μg/g (Pait et al., 2010). In Jobos Bay, 

the mean cadmium concentration was 0.01 μg/g, similar to 

southwest Puerto Rico (Apeti et al., 2012b). The NS&T 

median for cadmium in sediments is 0.19 μg/g, the 85th 

percentile is 0.44 μg/g. All three sites in the STEER where 
STEER Sediment Contaminants and Bioeffects Report

p. 26 26Results and Discussioncadmium was detected from the stratifi ed random sampling 

were at or above the NS&T median, but below the 85th 

percentile. Three of the four sites from the 2010 targeted 

sampling were also above the NS&T median, but all were 

below the 85th percentile. 

NOAA Sediment Quality Guidelines for Cadmium. Figure 

15 also contains the NOAA ERL and ERM. All cadmium 

levels detected in the STEER sediments, either from the 

stratifi ed random sampling or from the 2010 targeted sampling, were below the ERL. 

Cadmium is used in a number of applications, including 

nickel-cadmium (Ni-Cd) 

batteries, paint pigments 

and in electroplating (Ellor and Stemniski, 2007). 

Sites 1-1P and 1-3P are 

both in Mangrove Lagoon, which is adjacent 

to the Bovoni Landfi ll, 

and could be one source 

for the cadmium. At 

this time, it is not known 

whether the cadmium 

detected is associated 

with runoff or subsurface 

fl ow from the landfi ll, or 

perhaps input from septic 

systems or runoff from 

residential areas. At 

one time, a wastewater 

treatment plant emptied 

directly into Mangrove 

Lagoon (Grigg et al., 

1971). Additional work 

is needed to better assess 

the possible sources of 

cadmium to the area of 

Mangrove Lagoon and 

Benner Bay. 

Effects of Sediment Grain Size. Because of the low number of cadmium detections, an assessment of the effects of 

grain size and TOC was not carried out. 

Chromium. The concentrations of chromium detected 

in the sediments collected from the STEER are shown in 

Figure 16. Higher concentrations were detected in the 

Mangrove Lagoon and Benner Bay areas, a pattern similar 

to a number of the organic compound classes (e.g., PAHs, 

PCBs) analyzed for this project. 

The mean concentration of chromium in the STEER from 

the stratifi ed random sampling was 14.1 ±1.76 μg/g; the 

median was 11.4 μg/g. The highest concentration of chromium in the sediments analyzed from the stratifi ed random 

sampling was 35.7 μg/g at site 1-1P in Mangrove Lagoon. 

The second highest concentration, 32.3 μg/g, was also in 

Mangrove Lagoon at site 1-3P. The three highest levels 

of chromium from the stratifi ed random sampling were all 

from Mangrove Lagoon. The lowest level of chromium 

detected from the stratifi ed random sampling was at 2-24A 

(4.91 μg/g). 

Figure 16 also contains the results of the targeted sampling 

in 2010. The highest chromium concentration detected was 

40.4 μg/g at BB-2, similar to the concentration of chromium at the sites in Mangrove Lagoon. 

Variation of Chromium Across Strata. An ANOVA carried 

out on the log10 transformed data indicated that chromium 

varied signifi cantly (p = 0.0090) by stratum. A subsequent 

pair wise comparison (Tukey HSD) indicated that Stratum 

1 was signifi cantly different (higher) from Strata 3, 4 and 

5, however, Stratum 2 (Benner Bay) was not signifi cantly 

different from Stratum 1. 

Figure 15. Cadmium detected in sediments from the St. Thomas East End Reserves.
STEER Sediment Contaminants and Bioeffects Report

p. 27 27Results and Discussion

Figure 16. Chromium detected in sediments from the St. Thomas East End Reserves.

Comparison with Other Data. EPA’s EMAP analyzed four 

samples from the STEER in 2004. The mean concentration from these four samples was 3.06 μg/g, lower than the 

mean found in the current study in the STEER. The highest 

chromium concentration found in the STEER by EMAP 

was 4.8 μg/g. 

In southwest Puerto Rico, Pait et al. (2008) calculated 

a mean chromium 

concentration of 31.2 

μg/g, higher than 

in the STEER. In 

Vieques, mean chromium levels in the 

sediment were also 

somewhat higher, 

22.5 μg/g (Pait et al., 

2010). In Jobos Bay, 

the mean chromium 

concentration was 

18.3 μg/g (Apeti et 

al., 2012b), similar to 

what was found in the 

STEER. The NS&T 

median for chromium 

in sediments is 66 

μg/g, higher than any 

of the chromium levels found in sediments 

in the STEER in this 

study.

Chromium is used in 

a number of applications, including stainless steel production, chromium plating, and as a pigment. 

As with cadmium, it is not known if the chromium detected 

in the Mangrove Lagoon area is associated with inputs from 

the landfi ll, from septic systems, runoff from residential 

areas, or perhaps a combination of these sources. As noted, 

at one time a wastewater treatment plant emptied directly 

into Mangrove Lagoon (Grigg et al., 1971). 

NOAA Sediment Quality Guidelines for Chromium. The 

ERL and ERM for chromium are also included in Figure 

16. All STEER chromium values were below both of these 

NOAA guidelines. 

Effects of Sediment Grain Size. Using the log10 normalized data, chromium was found to be correlated with the 

percent fi nes (p = 0.0180). A nonparametric analysis 

showed this metal had a slightly higher correlation with 

percent clay (Spearman Rho = 0.5441, p = 0.0060) than the 

percent silt content (Spearman Rho = 0.4767, p = 0.0185). 

Copper. The results from the analysis of copper in the 

sediments from the STEER can be seen in Figure 17 and 

in Appendix H. The mean concentration of copper found 

in the sediments was 21 ±7.46 μg/g; the median was 3.75 

μg/g. The highest copper concentration from the stratifi ed 

random sampling was 155 μg/g at site 2-20P, followed by 

69.9 μg/g at site 1-1P in Mangrove Lagoon. 

From the targeted sampling in 2010, the lowest concentration was 60.6 μg/g at ML-10. At BB-1, the concentration 

of copper in the sediment was 145 μg/g. At BB-2, the copper concentration was very high, 1,010 μg/g. 

Copper has many applications including use in wire, 

electronic circuits, antifouling paints for boat hulls, copper 

plumbing, industrial catalysts, and in a number of alloys 

(e.g., brass). Copper sulfate is used in agriculture and as 

an anti-algal agent, although it is probably unlikely copper 

was used to any great extent agriculturally in the STEER 

watershed. 
STEER Sediment Contaminants and Bioeffects Report

p. 28 28Results and Discussion Variation of Copper Across Strata. A Kruskal-Wallis test 

run on the ranked values from the stratifi ed random sampling indicated a signifi cant difference (p = 0.0001) in the 

concentration of copper across the strata. A Tukey-Kramer 

HSD analysis indicated that copper did not vary signifi cantly between Strata 1 and 2, but were different from Strata 3, 

4, and 5. 

Comparison with Other Data. EPA’s EMAP collected and 

analyzed four sites within the STEER for copper in 2004. 

The mean concentration 

of copper in the sediments from the EMAP 

work was 3.9 μg/g, 

substantially less than 

the mean concentration 

found in the STEER in 

the current study. It is 

unclear why the means 

for the stratifi ed random 

sampling done in both 

studies were quite different, although it may 

be related to the greater 

number of samples 

taken in the current 

study, particularly in the 

Mangrove Lagoon area. 

As noted earlier, Mangrove Lagoon was not 

included in the EMAP 

work. 

In southwest Puerto 

Rico, Pait et al. (2008) 

detected a mean copper 

concentration of 5.21 

μg/g, lower than the 

mean in the STEER. In Vieques, the mean copper concentration was 25.9 μg/g, similar to the mean in the STEER 

sediments. In Jobos Bay, Apeti et al. (2012b) found a mean 

copper concentration of 34.1 μg/g, somewhat higher than 

the mean found in the STEER. 

The NS&T median for copper in sediments is 16 μg/g. 

From the stratifi ed random sampling in 2011, six sites (2-

20P, 1-1P, 1-3P, 1-2P, 2-16P, 1-5P), all either in Mangrove 

Lagoon or northern Benner Bay, had copper levels above 

the NS&T median. The NS&T 85th percentile for copper 

is 38.3 μg/g. Five of these sites had copper levels above 

the NS&T 85th percentile level. All four of the targeted 

samples were above the NS&T median and 85th percentile. 

Finally, the concentration in the sediment at BB-2, is one 

of the 10 highest concentrations of copper that has been 

detected in NOAA’s NS&T Program. 

NOAA Sediment Quality Guidelines for Copper. The 

ERL for copper is 34 μg/g (Figure 17); the ERM is 270 

μg/g. From the stratifi ed random sites, six sites (2-20P, 

1-1P, 1-3P, 1-2P, 2-16P, 1-5P) exceeded the ERL, but none 

exceeded the ERM for copper, indicating that more sensitive life stages in these areas could be experiencing effects 

related to the presence of copper. 

All four of the 2010 targeted sites (i.e., BB-1, BB-2, ML-2 

and ML-10) were above the NOAA ERL for copper. At 

Site BB-2 (1,010 μg/g), the level of copper substantially 

exceeded the copper ERM of 270 μg/g, indicating that effects from this trace element on biota inhabiting the sediments are likely. 

Copper in the Sediments in Northern Benner Bay and Mangrove Lagoon. The pattern of copper seen in the sediments 

in Mangrove Lagoon and Benner Bay, with higher concentrations in the northern part of Benner Bay, and somewhat 

lower concentrations in Mangrove Lagoon, suggests a posFigure 17. Copper detected in sediments from the St. Thomas East End Reserves.
STEER Sediment Contaminants and Bioeffects Report

p. 29 29Results and Discussion

sible gradient. The fl ow of water into and out of Mangrove 

Lagoon appears to have a number of driving forces, including a clockwise pattern through Cas Cay, a reversing tidal 

current, along with wind drift and runoff fl ow through both 

entrances (Tetra Tech, 2005). The three highest concentrations of copper were found at sites BB-1, 2-20P and BB-2, 

all in the northern part of Benner Bay. Given the variable 

direction of water currents in the area, a signifi cant source 

of the higher copper concentrations in the sediments could 

be from the northern part of Benner Bay. However, additional work would be needed to assess this possibility. 

Marinas and boat yards 

are a major commercial 

land use adjacent to 

the northern portion of 

Benner Bay. Copper has 

been used for years in 

antifoulant paint systems 

on boat hulls. Activities such as the mooring 

of vessels with hulls 

painted with coppercontaining bottom 

paints, along with the 

cleaning, scraping and 

repainting of boat hulls, 

and subsequent runoff 

containing paint chips 

and dust, as might occur 

during a rainstorm, could 

lead to elevated concentrations of this metal in 

the environment. The 

elevated levels of TBT 

in the sediments in this 

same part of Benner Bay 

and lower levels of TBT 

in Mangrove Lagoon support the possibility that the copper found in the sediments in the northern part of Benner 

Bay are related to the use of both copper and TBT over the 

years in boat-related activities. A nonparametric correlation 

analysis between copper and TBT in the STEER showed a 

signifi cant positive correlation (Spearman Rho = 0.7078, p 

= 0.0001). As noted earlier, TBT has had signifi cant use as 

an antifoulant on boat hulls. For copper, however, inputs of 

copper into Mangrove Lagoon from Turpentine Gut, runoff 

from residential areas, and inputs from the adjacent Bovoni 

Landfi ll could also be contributing sources. 

In any case, the concentration of copper at BB-2 is indicative of levels that are likely impacting benthic organisms in 

this area. As with TBT, additional work is needed to assess 

the extent of copper contamination both in surface sediments and in sediment cores, along with effects on biota. 

Effects of Sediment Grain Size. A nonparametric analysis 

revealed that copper was signifi cantly correlated with the 

percent fi nes (Spearman Rho = 0.7852, p < 0.0001) fraction 

of the sediments. 

Lead. The concentrations of the trace element lead detected 

in the STEER sediments are shown in Figure 18. The mean 

concentration was 5.87 ±1.90 μg/g; the median was 0.82 

μg/g. The highest concentration of lead in the sediments 

from the stratifi ed random sampling was 31 μg/g at 1-2P in 

Mangrove Lagoon. The lowest concentration detected was 

0.371 μg/g at 4-50P in Cowpet Bay. The highest concentration from the 2010 targeted sampling was 81.2 μg/g at 

BB-2 in Benner Bay (Figure 18, Appendix H). 

Variation of Lead Across Strata. A log10 transformation 

of the results failed to normalize the stratifi ed-random 

sampling data. The data were subsequently ranked, and a 

Kruskal-Wallis test on the ranked data showed a signifi cant 

(p <0.0001) difference in the concentration of lead across 

the STEER. A Tukey HSD test indicated that Stratum 

Figure 18. Lead detected in sediments from the St. Thomas East End Reserves.
STEER Sediment Contaminants and Bioeffects Report

p. 30 30Results and Discussion1 was signifi cantly higher than Strata 3, 4, and 5. The 

concentration of lead in Stratum 2 was not signifi cantly 

different from Stratum 1 or Stratum 3, but was signifi cantly 

higher than in Strata 4 and 5. 

Comparison with 

Other Data. The mean 

concentration of lead 

in the sediments in the 

STEER analyzed by 

EMAP was 1.02 μg/g, 

lower than the mean 

concentration found in 

the STEER in the current study. In southwest Puerto Rico, Pait 

et al. (2008) detected a 

mean lead concentration of 1.93 μg/g, less 

than that found in the 

STEER. In Vieques, 

the mean lead concentration was 5.42 μg/g, 

close to that in the 

STEER. In Jobos Bay, 

the mean concentration of lead in the sediments sampled was 

7 μg/g (Apeti et al., 

2012b), also similar to 

the STEER. 

The NS&T median 

sediment concentration 

for lead is 22.3 μg/g. Only two sites (1-2P and 1-3P) from 

the stratifi ed random sampling, both in Mangrove Lagoon, 

had lead levels above the NS&T median. The NS&T 85th 

percentile for lead is 39.1 μg/g. None of the sites in the 

STEER from the stratifi ed random sampling had a lead 

concentration in the sediments above this level. From the 

2010 targeted sampling, three of the four sites were above 

the NS&T median, with one site (BB-2) above the NS&T 

85th percentile. 

NOAA Sediment Quality Guidelines for Lead. The ERL for 

lead is 46.7 μg/g (Figure 18); the ERM is 216 μg/g. None 

of the randomly chosen sites had a concentration above the 

ERL. However, BB-2 (81.2 μg/g) from the 2010 targeted 

sampling had a concentration above the ERL, but still well 

below the ERM of 218 μg/g. 

Effects of Sediment Grain Size. A nonparametric correlation analysis between lead and percent fi nes in the sediment 

indicated a signifi cant positive correlation (Spearman Rho 

= 0.7643, p < 0.0001). 

Mercury. The concentrations of mercury detected in the 

sediments in the STEER are shown in Figure 19. The 

mean concentration of mercury in the sediments sampled 

in the STEER from the stratifi ed random sampling was 

0.019 ±0.01 μg/g; the median was 0.002 μg/g. The highest 

concentration of mercury found from the stratifi ed random 

sampling was in Mangrove Lagoon at site 1-1P (0.109 

μg/g). The second highest mercury detection was also 

in Mangrove Lagoon at site 1-3P (0.081 μg/g). From the 

2010 targeted sampling, the highest concentration found 

was at BB-2 (0.34 μg/g) in northern Benner Bay. As with a 

number of the other contaminants, higher concentrations of 

mercury were found in northern Benner Bay and in Mangrove Lagoon.

Mercury is found in crustal materials, and natural erosional 

processes can contribute to its presence in the marine environment, in addition to anthropogenic inputs. Coal-burning 

power plants are the largest human-caused source of mercury emissions to the air in the United States, accounting 

for over 50 percent of all domestic human-caused mercury 

Figure 19. Mercury detected in sediments from the St. Thomas East End Reserves.
STEER Sediment Contaminants and Bioeffects Report

p. 31 31Results and Discussion

emissions (Eisler, 1987). As noted earlier, although many 

uses of mercury have been discontinued, mercury is currently used in fl uorescent light bulbs and in various electrical switches. 

Variation of Mercury Across Strata. A Kruskal-Wallis test 

run on the ranked mercury values indicated a signifi cant 

difference (p <.0001) between strata, and a TukeyHSD test indicated that 

Strata 1 and 2 were higher 

than Strata 3,4, and 5.

Comparison with Other 

Data. Mercury was not 

detected by EMAP in the 

sediments in the STEER. 

The mean sediment 

concentration of mercury 

found in southwest Puerto 

Rico was 0.004 μg/g. In 

Vieques, Pait et al. (2010) 

found a mercury concentration of 0.019 μg/g, the 

same as in the STEER. 

Apeti et al. (2012b) detected a mean concentration of 0.042 μg/g mercury in sediments from 

Jobos Bay, higher than 

was found in the STEER. 

The NS&T median for 

mercury is 0.062 μg/g. 

There were five sites from 

the 2011 stratified random 

sampling that were above the NS&T median; all four sites 

from the 2010 targeted sampling were above the NS&T 

median. Site BB-2 (0.34 μg/g) was above the NS&T 85th 

percentile of 0.20 μg/g. 

NOAA Sediment Quality Guidelines for Mercury. NOAA 

has established both ERL and ERM values for mercury, 

which are included in Figure 19. There was one exceedence of the ERL for mercury (0.150 μg/g) at BB-2 in 

northern Benner Bay, with a concentration of 0.34 μg/g, 

twice as high as the ERL, but below the ERM. 

Effects of Sediment Grain Size. A nonparametric correlation between mercury and the percent fines of the sediment 

indicated a significant positive correlation (Spearman Rho 

= 0.8116, p <.0001) between mercury and the smaller grain 

sizes of the sediments sampled in the STEER. 

Nickel. The concentrations of nickel detected in the sediments in the STEER are shown in Figure 20. The mean 

concentration of nickel from the stratifi ed random sampling 

was 6.53 ±0.57 μg/g and the median was 5.08 μg/g. The 

highest concentration of nickel found from the stratifi ed 

random sampling was in Mangrove Lagoon at site 1-1P 

(15.1 μg/g). The second highest nickel detection was also 

in Mangrove Lagoon at site 1-2P (11.6 μg/g). In fact, four 

of the highest nickel detections were in Mangrove Lagoon. 

From the 2010 targeted sampling, the highest concentration 

found was at ML-2 (13.5 μg/g) also in Mangrove Lagoon. 

As with other trace elements, nickel is found in crustal 

materials, and natural erosional processes can contribute 

to its presence in the marine environment, in addition to 

anthropogenic inputs. 

Variation of Nickel Across Strata. As part of the analysis, an assessment was completed to look at the variation 

of nickel among strata. A Kruskal-Wallis test run on the 

ranked nickel values, however, indicated no signifi cant difference (p= 0.1395) between strata.

Comparison with Other Data. EPA’s EMAP collected sediments from four sites located within the STEER. The mean 

concentration of nickel in the sediments at these four sites 

Figure 20. Nickel detected in sediments from the St. Thomas East End Reserves.
STEER Sediment Contaminants and Bioeffects Report

p. 32 32Results and Discussionwas 1.75 μg/g, lower than the mean found in the current 

study (6.53 μg/g). Even if the sites from Mangrove Lagoon 

are excluded, the mean concentration of nickel found in 

the sediments in the STEER outside of Mangrove Lagoon 

was 5.49 μg/g. The mean sediment concentration of nickel 

found in southwest Puerto Rico was 26.6 ±14.1, due in part 

to some substantially elevated levels at two sites within 

Guanica Bay (Pait et al., 2008). If the two sites in Guanica 

Bay are left out of the calculation, the mean concentration in the study area in southwest Puerto Rico was 6.48 

±1.03 μg/g, similar to what was found in the STEER. In 

Vieques, Pait et al. (2010) found a nickel concentration of 

7.80 ±1.07 μg/g, again similar to the STEER. Apeti et al. 

(2012b) detected a mean concentration of 10.2 μg/g nickel 

in sediments from Jobos Bay, higher than was found in the 

STEER. The NS&T median for nickel is 25.1 μg/g, higher 

than any concentration found in the STEER, either through 

the stratified random 

or the targeted sampling. 

NOAA Sediment 

Quality Guidelines 

for Nickel. NOAA 

has established both 

ERL and ERM values 

for nickel, which are 

included on Figure 

20. All of the sediment samples from 

the STEER were 

below the ERM and 

the ERL. However, 

a number of sites 

within Mangrove 

Lagoon, particularly 

1-1P (15.1 μg/g), approached the ERL. 

Effects of Sediment 

Grain Size. A nonparametric correlation 

between nickel and 

the percent fines of 

the sediment indicated a significant positive correlation (Spearman Rho = 

0.6583, p = 0.0005) between nickel and the smaller grain 

sizes of the sediments sampled in the STEER. 

Zinc. The results of the analysis of zinc in the sediments 

collected in the STEER are shown in Figure 21. The mean 

zinc concentration in the sediments from the stratifi ed random sampling was 37.3 ±10.7 μg/g; the median was 11.1 

μg/g. The highest concentration of zinc from these collections was found at site 1-2P, at 159 μg/g. The second highest zinc concentration from the stratifi ed random sampling 

was also in Mangrove Lagoon at site 1-3P, with a concentration of 154 μg/g.

From the 2010 targeted sampling, the highest zinc concentration detected was 392 μg/g in Benner Bay (BB-2), followed by 192 μg/g in BB-1, also in Benner Bay. As with 

a number of the other contaminants included in this report, 

higher concentrations were found in northern Benner Bay 

and in Mangrove Lagoon. 

Variation of Zinc Across Strata. A Kruskal-Wallis test on 

the ranked values from the stratifi ed random sampling indicated zinc varied signifi cantly (p = 0.0006) by stratum, and 

the Tukey-Kramer HSD test indicated that Stratum 1 and 2 

were signifi cantly different (higher) from Stratum 5. 

Comparison with Other Data. The mean for the four 

samples that EPA’s EMAP collected outside of Mangrove 

Lagoon in the STEER was 5.8 μg/g, substantially below 

the mean for the STEER in the current project. If the 

samples within Mangrove Lagoon are left out, the mean for 

Figure 21. Zinc detected in sediments from the St. Thomas East End Reserves.
STEER Sediment Contaminants and Bioeffects Report

p. 33 33Results and Discussion

the STEER is 18.4, still higher than was found by 

EMAP. 

The concentration of zinc detected in the STEER 

can also be compared with work completed in 

southwest Puerto Rico. Pait et al. (2008 ) detected a 

mean zinc concentration of 8 μg/g, below the mean 

found in the STEER. In Vieques, Pait et al. (2010) 

calculated a mean zinc concentration of 34.4 μg/g, 

similar to what was found in the STEER. In Jobos 

Bay, Apeti et al. (2012b) found a mean zinc concentration of 54.7 μg/g, somewhat higher than what 

was found in the STEER. 

The NS&T median for zinc is 74 μg/g; the 85th 

percentile is 143 μg/g. From the stratifi ed random 

sampling, there were six sites above the NS&T median, and two sites (1-2P and 1-3P) above the NS&T 

85th percentile (Appendix H.). From the 2010 

targeted sampling, three (BB-2, BB-1, and ML-2) of 

the four sites analyzed were above the NS&T 85th 

percentile. 

NOAA Sediment Quality Guidelines for Zinc. The 

ERL for zinc is 150 μg/g. There were two sites 

(1-2P and 1-3P) from the stratifi ed random sampling 

that exceeded the ERL. From the 2010 targeted 

sampling, three of the four sites (BB-2, BB-1, and 

ML-2) analyzed exceeded the ERL. The results of 

this analysis indicate that some of the more sensitive species or life stages in both Benner Bay and 

Mangrove Lagoon could begin to experience effects 

related to the elevated levels of zinc. In addition, 

any additive effects that may be present as a result 

of multiple contaminants (e.g., TBT and copper) 

from this area are unknown. None of the sites 

exceeded the ERM, however, BB-2 (392 μg/g) from 

the 2010 targeted sampling was fairly close to the 

zinc ERM of 410 μg/g. 

Effects of Sediment Grain Size. Finally, the nonparametric Spearman’s analysis between zinc and 

the sediment percent fines indicated a significant 

positive correlation (Spearman Rho = 0.5678, p = 

0.0038) between zinc and the smaller grain sizes of 

the sediments sampled in the STEER. The correlation between zinc and percent clay (Spearman Rho 

= 0.7270, p < 0.0001) appeared somewhat higher 

than silt (Spearman Rho = 0.5235, p = 0.0038).

Normalization of Trace Elements. The range of 

concentrations of individual metals was highly 

y = 0.0009x + 9.7847

r2 = 0.7786

0.0

10.0

20.0

30.0

40.0

50.0

60.0

70.0

80.0

0 10000 20000 30000 40000 50000 60000 70000

% Fines

Al

a

y = 0.649x - 276.26

r2 = 0.9992

0

5000

10000

15000

20000

25000

30000

35000

40000

45000

0 10000 20000 30000 40000 50000 60000 70000

Fe

Al

b

Figure 22. Normalization of aluminum to %fi nes (a), aluminum to iron (b), aluminum to chromium (c) and calcium to 

chromium (d) in sediments from the STEER.

y = -5E-05x + 28.545

R2 = 0.4251

0

5

10

15

20

25

30

35

40

0 100000 200000 300000 400000 500000

Cr

Ca

d

y = 0.0004x + 8.3794

R2 = 0.8743

0

5

10

15

20

25

30

35

40

0 10000 20000 30000 40000 50000 60000 70000

Cr

Al

c
STEER Sediment Contaminants and Bioeffects Report

p. 34 34Results and Discussionvariable across the STEER (Appendix H). Copper concentrations varied by a factor of up to 119, 

while nickel varied only by a factor of 3.5. Silver 

was not detected at any site. Cadmium, antimony, 

and elemental tin were above detection limits only 

in Mangrove Lagoon and one or two locations in 

Benner Bay. 

Copper and zinc were above ERLs at one or more 

sites, but none exceeded an ERM level at any of the 

randomized sites. BB-2 from the 2010 sampling 

did exceed the ERM level for copper. Metal concentrations are generally correlated with sediment 

grain size. 

Concentrations of aluminum, iron, and trace metals 

correlate well with concentrations of the percent 

fines because concentrations of both aluminum and 

most metals are very low in coarse-grained quartz 

sand or carbonate shell material and much higher in 

fine-grained aluminosilicates (Figure 22a). Aluminum and iron in sediments are derived from terrestrial sources resulting from watershed erosion and 

are rarely introduced above background levels by 

anthropogenic activities other than metal production facilities. They are present at percent levels in 

most sediment as opposed to part per million levels 

for trace metals and exhibit a very close relationship (Figure 22b). Because the metals are primarily 

derived from terrestrial erosion, sediment aluminum 

has a much closer relationship to the trace metals 

such as chromium (especially in fine grained sediment) than sediment calcium because the origin of 

the calcareous sands is not terrestrial (Figure 22c 

and d). 

Coarse grained sediments generally contain high 

levels of silica or carbonate depending on their origin. In temperate systems, silica is the predominant 

element in coarse sand and exhibits an inverse relationship with aluminum or iron, which predominate 

in fine grained sediment. In tropical island systems, 

sources of silicates are limited, and the dominant 

source of coarse grained sediments is calcium 

carbonate from organic sources. Aluminum and 

calcium thus have an inverse relationship (Figure 

23a). For this study, concentrations of trace metals 

were normalized to Al to assess locations where 

unusually high concentrations of trace metals may 

indicate anthropogenic inputs, above that expected 

as background. The relationships between aluminum and copper, zinc, and mercury can be seen in 

y = -4.2023x + 341146

r2 = 0.5205

0

50000

100000

150000

200000

250000

300000

350000

400000

450000

0 10000 20000 30000 40000 50000 60000 70000

Ca

Al

Figure 23. Normalization of aluminum to calcium (a), aluminum 

to copper (b), aluminum to zinc (c), and aluminum to mercury (d) 

in sediments from the STEER.

a

y = 0.0013x + 2.9725

r2 = 0.4757

0

20

40

60

80

100

120

140

160

180

0 10000 20000 30000 40000 50000 60000 70000

Cu

Al

b

y = 0.0026x + 1.5863

r2 = 0.9101

0

20

40

60

80

100

120

140

160

180

0 10000 20000 30000 40000 50000 60000 70000

Zn

Al

c

y = 2E-06x - 0.0031

r2 = 0.9143

-0.020

0.000

0.020

0.040

0.060

0.080

0.100

0.120

0 10000 20000 30000 40000 50000 60000 70000

Hg

Al

d
STEER Sediment Contaminants and Bioeffects Report

p. 35 35Results and Discussion

Figure 23 b-d, respectively. It is evident 

that copper, zinc, and 

mercury are found at 

a few selected sites at 

concentrations above 

that which would be 

predicted based upon 

background aluminum 

levels. All of these 

sites are in either 

Mangrove Lagoon 

or Benner Bay. It 

should also be noted 

that the concentrations of aluminum and 

iron are considerably 

higher in Mangrove 

Lagoon and Benner 

Bay than in the other 

strata, indicating that 

terrestrial sources of 

sediment are more 

dominant there than in 

the rest of the STEER. 

Additional regressions 

of aluminum and calcium versus the trace 

elements can be found in Appendix I. 

Clostridium perfringens. Although this species bacteria 

is not a chemical contaminant, it is often included in the 

analyses done by NOAA’s NS&T Program. This anaerobic, gram-positive staining rod-shaped bacteria frequently 

occurs in the intestines of humans, as well as in domestic 

and wild animals, and has been used as a sewage indicator. 

The results of the analysis of sediments for C. perfringens 

are shown in Figure 24 and in Appendix J. Higher levels of 

C. perfringens were found primarily in Mangrove Lagoon, 

with lower concentrations in most other locations. 

To assess the presence of viable C. perfringens, sediment 

extracts are plated on growth medium and the number of 

colonies that develop are counted. The mean C. perfringens concentration in the sediments was 291 ±167 CFU/g 

(colony forming units per gram of dry sediment). The sediment sample from 1-2P contained 3,493 CFU. Site 1-3P 

had a C. perfringens count of 2,137 CFU/g. Both 1-2P 

and 1-3P are near the mouth of Turpentine Gut, as it enters 

Mangrove Lagoon, which may be indicative of input from 

septic systems, domestic animals such as dogs, and from a 

nearby horse race track. From the 2010 targeted sampling, 

the highest concentration of C. perfringens found was at 

ML-10, also at the mouth of Turpentine Gut (2,558 CFU/g).

Variation of C. perfringens Across Strata. A Kruskal-Wallis 

test run on the ranked C. perfringens data indicated a signifi cant difference (p < 0.0001) between strata. A Tukey 

HSD test indicated that Strata 1 and 2 were signifi cantly 

different (higher counts) from Strata 3, 4 and 5. 

An analysis of C. perfringens and grain size was also 

carried out. A strong (p = 0.0010) correlation was found 

between the log10 normalized C. perfringens data and percent fi nes. A nonparametric analysis indicated a signifi cant 

negative correlation between C. perfringens and percent 

sand (Spearman Rho = -0.6342, p = 0.0009), and no correlation between C. perfringens and percent gravel (Spearman Rho = 0.1907, p = 0.3722). 

 

Sediment Quality Guidelines and C. perfringens. No 

NOAA or other health guidelines exist for C. perfringens

in sediments. C. perfringens is a common cause of foodborne illnesses. A more severe form of the disease can be 

fatal and results from ingesting large numbers of the active 

bacteria, typically from food. C. perfringens also has the 

capability of forming spores which can persist in soils and 

sediments. 

Figure 24. Clostridium perfringens detected in sediments from the St. Thomas East End Reserves.
STEER Sediment Contaminants and Bioeffects Report

p. 36 36Results and Discussion

Figure 25. Amphipod mortality vs % sand and gravel 

in St. Thomas STEER sediments. 

0

20

40

60

80

100

0 20 40 60 80 100

% Amphipod Mortality

% Sand & Gravel

Figure 26. Amphipod mortality versus % total organic 

carbon in the STEER sediments.

0

20

40

60

80

100

0123456

% Amphipod Mortality

% TOC

Table 4. Toxicity bioassay summary results from the STEER.

Site

Amphipod Mortality (%) Different from Control

Sig

Sea Urchin 

Fertilization Failure (%) Different 

from Control

Sig P450 

Response

BaP Eq. 

(ng/g)

1-1P 10.31 23.7 * 4.94 5.64

1-2P 14.43 * 14.5 * 13.79 12.98

1-3P 4.12 8.2 14.24 44.83

1-4P 7.22 6.3 9.86 0.12

1-5P 15.46 97.6 * 15.66 0.80

2-16P 12.37 * 40.4 * 11.12 8.33

2-19P 4.12 2.9 2.39

2-20P 8.25 0.0 13.35 1.78

2-24A 13.40 5.1 2.88

3-32P 10.31 15.5 * 15.64 8.58

3-33P 7.22 65.9 * 2.47

3-37A 10.31 9.2 3.36

3-38A 7.22 0.0 4.76 2.03

3-45A 47.42 * 0.0 2.49

4-46P 29.90 * 30.5 * 2.20

4-47P 21.65 * 13.8 2.75

4-48P 12.37 13.3 1.23

4-49P 10.31 18.2 * 2.73

4-50P 37.11 * 6.8 1.49

5-61P 9.28 0.0 1.45

5-62P 22.68 * 3.6 1.90

5-70A 53.61 * 0.2 5.57

5-71A 4.12 5.8 3.14 0.97

5-75A 28.87 * 13.6 2.15

* - statistically signifi cant from control 

The high levels of C. perfringens

within Mangrove Lagoon indicate 

there is a need to reduce wastewater, stormwater and various sources 

of inputs for this pathogen, and 

other pathogenic microorganisms 

that may be present as well. Reducing the levels of bacterial contamination would not only benefi t 

ecological health, but human health 

as well.

Sediment Toxicity

The use of sediment toxicity bioassays, along with the benthic infaunal community analysis, provides 

important information on the 

impacts of the chemical contaminants found in the STEER sediments. While the NOAA ERMs 

and ERLs provide an indication of 

the likelihood of effects from one 

chemical contaminant or chemical contaminant class, the bioassays (and the benthic community 

analysis) integrate the effects of all 

contaminants present along with 

other environmental parameters. 

For this project, the sediment toxicity bioassays included amphipod 

(Ampelisca abdita) mortality, sea 

urchin (Arbacia punctulata) fertil-
STEER Sediment Contaminants and Bioeffects Report

p. 37 37Results and Discussion

Figure 27. P450 response vs PAH concentrations (a), P450 

response in terms of B[a]P eq for the subset of samples that 

exceeded the TCDD standard response (b). 

0

5

10

15

20

0 500 1000 1500

P450 response

total PAH ug/g

y = 0.0323x - 2.3609

R2 = 0.8181

0

10

20

30

40

50

0 500 1000 1500

BaP Eq

total PAH ug/g

b

a

ization impairment, and cytochrome P450 Human Reporter 

Gene System (HRGS) response tests. 

The bioassay results for all tests are summarized in Table 

4. All values are control corrected. Signifi cant amphipod 

mortality occurred throughout the STEER study area. The 

highest mortality values observed were in the eastern strata. 

This may be infl uenced by sediment grain size. The amphipod A. abdita normally live in silty sand habitats and may 

not thrive well in coarse sand (ASTM, 2008), however, this 

has not been tested rigorously. 

Amphipod Toxicity. All the amphipod bioassays with 

mortality elevated above 20% were in sediments that were 

greater than 60% sand and gravel (Figure 25). Other parameters (e.g. higher TOC) may ameliorate this effect. Most of 

the highly toxic amphipod results were in coarse sand with 

very low TOC (Figure 26). 

Table 5. Average (n = 3) P450 bioassay response following 6 

and 24 hour incubation with STEER sediment extracts. 

Site 6 Hour 

Response

24 Hour 

Response

1-1P 104.9 13.3

1-2P 113.3 24.7

1-3P 117.3 35.0

1-4P 78.5 10.4

1-5P 129.8 14.1

2-16P 89.7 22.6

2-19P 12.3 3.53

2-20P 113.4 29.0

2-24A 17.3 1.37

3-32P 134.4 41.0

3-33P 39.0 3.00

3-37A 21.6 9.24

3-38A 100.0 9.44

3-45A 39.8 5.22

4-46P 11.0 3.19

4-47P 16.1 3.28

4-48P 6.12 1.74

4-49P 15.9 1.86

4-50P 13.0 2.46

5-61P 11.9 0.30

5-62P 24.0 1.42

5-70A 42.0 3.84

5-71A 57.0 5.17

5-75A 30.6 3.26

clean 4.44 0.56

blank -1.39 0.10

spike 125.5 46.5

contam 123.2 55.9

Values are expressed as % of the 10nM TCDD standard 

response. QA/QC samples: blank = solvent blank; clean = 

uncontaminated site in the Chesapeake Bay; contam = contaminated site in Chesapeake Bay; spike = spiked solvent solution.

Sea Urchin Fertilization. Half of the signifi cant sea urchin 

fertilization bioassays were in sediment from Mangrove 

Lagoon or the canal joining it to Benner Bay (Table 4). Jersey Bay and St. James Bay also showed signifi cant results 

in two locations. 

P450. Most of the signifi cant P450 responses were in 

the western strata, including all of the Mangrove Lagoon 

sites. Further testing of those samples that exceeded 50% 
STEER Sediment Contaminants and Bioeffects Report

p. 38 38Results and Discussion

Figure 28. P450 response (normalized to standard 10nM TCDD) following 6 and 24 hour exposures to extracts from St. Thomas STEER sediment samples. (QA/QC samples; blank=solvent 

blank; clean=uncontaminated site in Chesapeake Bay; contam.=contaminated site in Chesapeake Bay; spiked solvent solution). 

of the 10 nM TCDD 

standard are also 

presented in Table 4 

in terms of B[a]P eq. 

The P450 response 

in terms of B[a]P eq 

is strongly correlated 

with PAH concentrations (Figure 27). 

Results of the timed 

exposure (6 vs 24 

hrs) to test for the 

relative contribution 

of labile versus persistent contaminants 

are shown in Table 5. 

In all cases, the 6 hr 

incubation showed a 

higher response than 

the 24 hr incubation 

(Figure 28). This also 

indicates that the predominant chemical 

classes the cells were 

responding to were 

PAHs, as they are 

more easily degraded 

than the more recalcitrant PCBs. It is 

noteworthy that the level of response in Mangrove Lagoon 

and portions of Benner Bay and Cowpet Bay exhibit initial 

responses as high as the spiked sample and the positive 

control. 

Taken together, the bioassay results indicate a signifi cant 

gradient of effect from west to east within the STEER 

(Figure 29). Toxic responses occurred in all strata, but 

the western portion of the study area exhibited signifi cant 

results from multiple bioassays. As noted above, several 

of the amphipod bioassay results may be an artifact of the 

coarse coralline sediment present in many of the eastern 

sites (Strata 4 and 5, Appendix B). 

With the exception of TBT and copper, extremely high concentrations of individual chemical pollutants were not seen. 

However, the observed widespread toxicological responses 

indicate the interaction of a variety of factors, including 

multiple contaminants, physicochemical characteristics 

of the sediment, and likely chemical pollutants beyond 

the standard list of analytes that may vary from stratum to 

stratum. Additional statistical correlation analyses are in 

progress.

Benthic Community Analysis 

A total of 10,926 organisms were enumerated, comprised 

of 434 taxa (species or higher taxonomic level). Following elimination of epibenthic species (dwelling on hard 

surfaces, not within the sediment) and ‘artifi cial’ species 

(see page 13), there were 333 taxa and 10,605 individuals 

for analysis. There were 168 rare and unique taxa. One 

hundred fi fty seven taxa were found at only one location. 

Annelids were the dominant taxa, accounting for 59.2% of 

all the organisms. Mollusks and arthropods accounted for 

19.2 and 15.7%, respectively. Less than 1% of the animals 

were echinoderms. Throughout the STEER, abundance 

was dominated by two dozen taxa that were found throughout most strata and a large number of taxa only represented 

by a few individuals (Figure 30). 

Abundance was more uniform on average than diversity or 

number of species, but some locations had extremely low 

abundance and some sites were extremely high (Figure 31). 

Site 1-1P in Mangrove Lagoon only had 4 species and fi ve 

organisms in total. Site 2-16P had over 1,000 organisms. 
STEER Sediment Contaminants and Bioeffects Report

p. 39 39Results and Discussion

Figure 29. Distribution of bioassays showing responses that were signifi cantly different than controls or greater than a 

standard threshold (P450) in St. Thomas STEER sediments. 

Figure 30. Plot of total abundance of each taxa used in the analyses. Each triangle represents the total 

abundance of each individual taxa collected in the STEER. 

Gradients of 

diversity and 

species richness were seen 

from low in the 

west to higher 

in the eastern 

strata (Figure 

32). With two 

exceptions 

(Sites 1-4P and 

2-19P), diversity was higher 

in the eastern 

strata than 

in Mangrove 

Lagoon and 

Benner Bay. 
STEER Sediment Contaminants and Bioeffects Report

p. 40 40Results and Discussion

Figure 31. Total animal abundance at each station in the STEER.

Figure 32. Total number of species (taxa) and calculated diversity at each station in the STEER.

These are refl ected in the calculated correlation coeffi cients. Number of species 

and diversity were negatively correlated 

with the ERMq, (Table 6). The ERMq is 

calculated by dividing the concentration of 

each contaminant analyzed in the sediment 

by its available ERM to produce a quotient. 

Number of species and diversity were positively correlated with stratum. There were 

no signifi cant correlations with amphipod 

mortality or sea urchin fertilization failure. 

The number of species and diversity were 

signifi cantly and negatively correlated with 

the PAH benzo[a]pyrene concentrations. A 

similar pattern was seen with respect to the 

percentage of fi nes in the sediments, and 

sand plus gravel showed the inverse. 

Nodal Analysis. The nodal analysis revealed two site 

groups and three species groups. The site groups divided 

cleanly between 

Stratum 1 and 2 

(Mangrove Lagoon 

and Benner Bay) vs 

3, 4, and 5. There was 

almost no overlap in 

species makeup between the site groups. 

In Mangrove Lagoon 

and Benner Bay, there 

were 25 species, versus 109 species found 

in the other three strata. Species that were 

found in Mangrove 

Lagoon and Benner 

Bay were generally 

rarely found or were 

completely absent in 

the other three strata, 

and vice versa. The 

three species groups 

corresponded to the 

site groups. Mangrove 

Lagoon and Benner 

Bay have a different 

species assemblage 

than the other three 

strata, and were dominated by polychaete 

worm species that are 

neither widespread nor numerous in the rest of the STEER. 

Strata 3, 4 and 5 shared a common assemblage of species. 
STEER Sediment Contaminants and Bioeffects Report

p. 41 41Results and Discussion

Table 7. Results of SIMPER analysis. Taxa highlighted in green were cosmopolitan and were 

found in all strata. Taxa highlighted in yellow were found in strata 1 and 2. 

Stratum 1 Stratum 2 Excluded Sites

Index 

Value Species

Index 

Value Species

Index 

Value Species

23.8 Tubifi cidae (lpil) 15.3 Tubifi cidae (lpil) 6.11 Tubifi cidae (lpil)

13.07 Macoma brevifrons 14.83 Mediomastus (lpil) 5.32 Prionospio heterobranchia

6.23 Prionospio heterobranchia 14.01 Prionospio heterobranchia 4.65 Schistomeringos pectinata

5.98 Podarkeopsis levifuscina 11.95 Nemertea (lpil) 4.65 Branchiomma nigromaculata

5.56 Caecum pulchellum 11.64 Cirrophorus lyra 4.65 Maldanidae (lpil)

4.71 Exogone verugera 7.19 Podarkeopsis levifuscina 4.47 Podarkeopsis levifuscina

4.01 Nemertea (lpil) 3.68 Schistomeringos pectinata 4.47 Sabellidae (lpil)

3.99 Mediomastus (lpil) 3.66 Pseudopolydora (lpil) 4.27 Cumella (lpil)

3.94 Naineris setosa 3.08 Scoletoma verrilli 4.27 Leptochelia forresti

3.89 Pseudopolydora (lpil) 2.87 Syllis cornuta 4.27 Nemertea (lpil)

3.83 Caulleriella cf. alata 2.6 Aoridae (lpil) 4.27 Syllis cornuta

3.67 Podarke obscura 2.59 Capitella capitata 3.76 Chione cancellata

3.58 Sphaerosyllis piriferopsis 2.41 Exogone verugera 3.76 Mesanthura bivittata

1.89 Sabellidae (lpil) 2.18 Nereis acuminata 3.76 Cirratulidae (lpil)

1.81 Grandidierella bonnieroides 2.03 Schistomeringos rudolphi 3.76 Terebellidae (lpil)

Parameter Statistics ERMq Stratum Amphipod 

Mortality

Fertilization 

Failure B[a]P %Silt and %Clay (Fines)

%Sand and 

%Gravel

Species Spearman Rho -0.65154 0.44292 0.12172 -0.25736 -0.64343 -0.62068 0.62068

Signifi cance 0.0006 0.0302 0.571 0.2247 0.0007 0.0012 0.0012

Abundance Spearman Rho 0.16565 0.04081 0.13534 -0.16166 -0.01359 0.01913 -0.01913

Signifi cance 0.4392 0.8498 0.5283 0.4505 0.9497 0.9293 0.9293

Diversity Spearman Rho -0.56542 0.47125 0.22625 -0.24324 -0.65588 -0.55937 0.55937

Signifi cance 0.004 0.0201 0.2877 0.2521 0.0005 0.0045 0.0045

Table 6. Spearman Rank correlation coeffi cients (bold) and signifi cance level for community parameters and selected 

physical and chemical parameters, and toxicological results. 

The third group of 26 species were found at sites 1-4P and 

2-19P (hereinafter referred to as excluded sites). These 

species were rarely found elsewhere in either Mangrove 

Lagoon and Benner Bay, or the other three strata. These 

two sites had a unique species assemblage, different from 

the other areas. Site 1-4P in the lower part of Mangrove 

Lagoon away from the infl uence of Turpentine Gut and the 

landfi ll, and 2-19P in central Benner Bay have sediment 

that is predominantly sand, unlike most of the other sites in 

those strata. These two locations shared a number of species found within Strata 1 and 2, but also another set of species that were much more diverse and included polychaetes, 

crustaceans, bivalves and snails. Again, the dominant 

species in these two sites are unlike the dominants in Strata 

1 and 2, and the 

other strata in the 

STEER (Tables 7 

and 8) as well.

SIMPER Analysis. 

The difference in 

dominant species 

between strata is 

also illustrated in 

the results from 

the SIMPER 

analysis. Figure 

33 shows the similarity index values 

for Strata 1 and 

2 (Mangrove Lagoon and Benner 

Bay, respectively), 

and the values for 

the excluded sites 

(excluded from 

the Stratum 1 and 2 lists), ranked from highest to lowest. 

Only a small number of species have high scores in Strata 1 

and 2. That is, only a few are dominant. In contrast, none of 

the species in the two excluded sites have high scores. They 

are all equally important in defi ning the community makeup. The top 15 species in each group are listed in Table 7. 

Species highlighted in yellow were found in both Strata 1 

and 2 (the colors are arbitrary). The strata have very similar 

dominant species makeup (there are many overlapping species that have high index values in both strata). Only two 

of the top species found in the excluded sites were present 

in both Strata 1 and 2. Thus, the species that are considered 

‘typical’ in Strata 1 and 2 were generally not ‘typical’ in the 
STEER Sediment Contaminants and Bioeffects Report

p. 42 42Results and Discussion

Figure 33. Results of the SIMPER analysis for Strata 1-2. Figure 34. Results of the SIMPER analysis for Strata 3-5.
STEER Sediment Contaminants and Bioeffects Report

p. 43 43Results and Discussion

Table 8. Top species in each stratum. Taxa highlighted in green were cosmopolitan and were found in all strata. Taxa 

highlighted in blue were found in strata 3, 4, and 5.

Stratum 3 Stratum 4 Stratum 5 Excluded Sites

Index 

Value Species

Index 

Value Species

Index 

Value Species

Index 

Value Species

5.01 Nemertea (lpil) 5.44 Nemertea (lpil) 6.83 Nemertea (lpil) 6.11 Tubifi cidae (lpil)

4.47 Galathowenia oculata 5.42 Exogone lourei 6.4 Lucinidae (lpil) 5.32 Prionospio heterobranchia

4.05 Exogone lourei 5.22 Tubifi cidae (lpil) 5.1 Tubifi cidae (lpil) 4.65 Schistomeringos pectinata

4.02 Prionospio (lpil) 4.82 Lucinidae (lpil) 4.97 Prionospio steenstrupi 4.65 Branchiomma nigromaculata

3.84 Armandia maculata 4.79 Heteropodarke formalis 4.94 Galathowenia oculata 4.65 Maldanidae (lpil)

3.69 Lucinidae (lpil) 4.52 Armandia maculata 4.82 Exogone rolani 4.47 Podarkeopsis levifuscina

3.59 Maldanidae (lpil) 3.21 Pionosyllis gesae 4.18 Cumella (lpil) 4.47 Sabellidae (lpil)

3.49 Ischyroceridae (lpil) 3.11 Pseudoleptochelia (lpil) 3.64 Aricidea taylori 4.27 Cumella (lpil)

3.4 Sipuncula (lpil) 2.96 Terebellidae (lpil) 3.62 Codakia (lpil) 4.27 Leptochelia forresti

2.48 Aspidosiphon (lpil) 2.89 Fabricinuda trilobata 3.47 Leptochelia (lpil) 4.27 Nemertea (lpil)

2.35 Fabricinuda trilobata 2.89 Caulleriella cf. alata 3.26 Xenanthura brevitelson 4.27 Syllis cornuta

2.34 Sphaerosyllis piriferopsis 2.87 Saltipedis (lpil) 3.13 Exogone lourei 3.76 Chione cancellata

2.33 Exogone dispar 2.85 Tellinidae (lpil) 3.1 Sipuncula (lpil) 3.76 Mesanthura bivittata

2.16 Ophiuroidea (lpil) 2.71 Protodorvillea kefersteini 2.81 Pitar simpsoni 3.76 Cirratulidae (lpil)

2.13 Ampharetidae (lpil) 2.68 Magelona sp. c 2.6 Armandia maculata 3.76 Terebellidae (lpil)

two excluded sites (1-4P and 2-19P). The taxa highlighted 

in green were found in all fi ve strata. Tubifi cids are a family of oligochaete worms. Nemerteans, also called proboscis worms, constitute an entire phylum. Both are diffi cult 

to identify to species without highly specialized expertise. 

Thus, these taxa actually represent potentially hundreds of 

species and are not particularly informative. Syllis cornuta

is a polychaete worm with a worldwide distribution. Thus, 

outside of these cosmopolitan taxa, the excluded sites had 

very little in common with the species makeup of Strata 1 

and 2. 

Figure 34 shows the indices for the species found in Strata 

3-5. The numbers of species in these strata are much higher 

than in Strata 1 and 2. All the scores are relatively low 

because of the much higher diversity than in Strata 1 and 

2, but the infl ection of the curves shows that the top 15-20 

species are the most important. Table 8 shows the top 15 

species in each stratum, plus the excluded sites (1-4P and 

2-19P) for comparison. Species names highlighted in blue 

were found in all three strata. Again, the taxa highlighted 

in green were cosmopolitan and are not informative. The 

species makeup of Strata 3, 4 and 5 is very similar. That is, 

the species highlighted in blue are typical in all three strata. 

The dominant species found in the excluded sites has almost no overlap with these strata. Thus there are three distinct species assemblages in the STEER. One in Mangrove 

Lagoon and Benner Bay, which are relatively depauperate. 

The two excluded sites that share some of the species found 

in Strata 1 or 2, but also another group of species not common anywhere else. The third assemblage is a much more 

diverse group, and occupies the bulk of the STEER area. 

Overall Patterns in the STEER Benthic Community. The 

average diversity and species richness is lower in Mangrove Lagoon and Benner Bay than the other strata, but 

abundance varies throughout the study area. Diversity and 

species richness are better indicators of stress than abundance, however. Extremely depressed abundance is indicative of highly stressed habitats, but marginally stressed areas may have as high or higher an abundance of organisms 

as healthy habitats, because those species that can thrive 

in stressed habitats may be released from competitive and 

predation pressure. Species in stressed environments also 

tend to have opportunistic and mobile life styles. 

The composition of species present in various locations is 

also an indicator of stressed habitats. Many authors consider amphipods and echinoderms to be relatively sensitive to 

contaminant stress (Long et al., 2001, Llanso et al., 2002). 

Similarly, several types of polychaetes, such as Spionids 

and Capitellids, and oligochaete tubifi cids, are considered 

to be tolerant of contamination and/or other stressful conditions, such as hypoxia (Lenihan and Micheli. 2001; Llanso 

et al., 2002). 

The community makeup of specifi c taxonomic groups 

in the different strata is shown in Table 9. Average total 

abundance of the large taxonomic groups was not informative. However, pollution tolerant species of annelids make 

up a much larger proportion of the organisms in Mangrove 
STEER Sediment Contaminants and Bioeffects Report

Summary and Conclusions

44

0.0

0.5

1.0

1.5

2.0

2.5

3.0

3.5

4.0

4.5

0

20

40

60

80

100

120

0.000 0.020 0.040 0.060 0.080 0.100 0.120 0.140

# Species

Diversity

Mean ERMq

Species

Diversity

Figure 35. Relationship between number of species and species diversity and the ERMq.

Table 9. Average per-station abundance of selected taxonomic groups in Mangrove Lagoon and 

Benner Bay without stations 1-4P and 2-19P, stations 1-4P and 2-19P together, and the remaining strata in 3 ( Nazareth Bay), 4 ( Cowpet/St. James Bay), and 5 (Great Bay). 

Lagoon and Benner Bay 

than in the two excluded 

sites or any other strata. 

The number of amphipods show the opposite 

pattern. 

Infl uence of Chemical 

Contamination on the 

Benthic Infaunal Community. Both species 

richness and diversity 

declined with ERMq 

(Figure 35). Likewise, 

species richness and 

diversity declined with 

increasing percent fi nes 

(percent silt+clay) in the 

sediment (Figure 36). 

The relationship between contaminants and 

muddy sediment is clear 

(Figure 37), but which 

is the causative factor for reduced species 

community condition 

cannot be determined 

from the data. Resident communities found in muddy 

areas are inherently different from the areas with coarser 

grained sediments. However, it is clear that the occurrence 

of signifi cant toxicity and the variety of signifi cant endpoints is highest in Mangrove Lagoon (Figure 29). Many 

of the signifi cant results from the amphipod bioassays are 

likely due to the coarse grain size of the sediments in the 

eastern strata. Consequently, amphipod mortality appears 

to be more widespread than the other toxicity endpoints. 

Abundance did not decline as sharply as species richness 

with increasing contamination, suggesting that 

pollution tolerant species are able to grow and 

reproduce in contaminated areas in the absence 

of competitors, predators, and/or indirect effects 

on the habitat. The weight of evidence between 

the toxicity, diversity, community makeup, 

and chemical contamination indicate pollution 

impacts in Benner Bay and, especially, in Mangrove Lagoon. 

Summary and Conclusions

The degradation of coral reef ecosystems 

worldwide has led to intensive efforts to understand and mitigate the stressors responsible for 

the declines of these ecosystems. The role of 

pollution is often cited as a major factor, but the 

degree to which pollution, and more specifi cally, 

chemical contaminants, impact coral reef and 

associated habitats is largely unknown. Because 

of this, coral reef managers may be missing an 

important, and in some locations, a critical piece 
STEER Sediment Contaminants and Bioeffects Report

Summary and Conclusions

45

Figure 36. Relationship between number of species and species diversity 

and percent fi nes. 

Figure 37. Relationship between mean ERMq and percent fi nes. 

of information required to effectively manage and, where needed, initiate restoration 

efforts.

For this project, a stratifi ed random 

sampling design was utilized to characterize the distribution and concentrations of 

chemical contaminants, toxicity, and the 

benthic infaunal community on an areal 

basis. This allows for a quantitative analysis of habitat condition between strata. The 

Sediment Quality Triad, or SQT approach, 

which combines three types of analyses, 

was used to provide a means for more 

holistically assessing the presence and impacts of anthropogenic stressors. Sediment 

samples for the analysis of both organic 

contaminants (e.g., polycyclic aromatic 

hydrocarbons (PAHs), polychlorinated 

biphenyls (PCBs) and pesticides), and inorganic contaminants (trace elements such 

as chromium, nickel and copper) were 

collected during a mission in June 2011. 

In 2010, a preliminary targeted sampling 

exercise resulted in the analysis of four of the sediment 

samples collected. 

Elevated levels of chemical contaminants were primarily 

found in Mangrove Lagoon and in northern Benner Bay. 

There is a large landfi ll adjacent to Mangrove Lagoon, that 

likely contributes a variety of contaminants through runoff, 

groundwater seeps, and perhaps from atmospheric deposition (e.g., from tire/trash fi res). Mangrove Lagoon also 

receives input from various commercial/industrial sources, 

as well as from adjacent residential/urbanized areas in the 

watershed via Turpentine Gut. Land use around northern 

Benner Bay appears dominated by marina-related activities, 

including the mooring, maintenance, and repair of boats, 

which is likely a source of chemical contaminants to the STEER.

Tributyltin, or TBT, was found at very high 

levels at three sites in the northern Benner Bay area (two from the targeted 2010 

sampling). The level of TBT detected at 

one site in Benner Bay was the third highest quantifi ed in NOAA’s NS&T Program. 

The presence of high concentrations of TBT 

likely represents the results of past application of TBT, mooring of vessels that contain 

TBT, along with the cleaning and scraping 

of hulls that may have had TBT applied at 

some point. Unfortunately, there are no established guidelines for TBT in sediment. A 

site specifi c numerical upper guideline established for an EPA Superfund site in the state 

of Washington was exceeded in northern 

Benner Bay. The purpose of the guideline 

developed was to inform EPA site manag-
STEER Sediment Contaminants and Bioeffects Report

Summary and Conclusions

46

ers when additional testing (e.g., toxicity testing) would be 

recommended. 

At the very least, additional analysis should be conducted 

in this area to better understand the distribution of TBT in 

surfi cial and deeper (cores) sediments, along with additional toxicity testing in the area. This is particularly needed 

if any of these areas are dredged in the future to deepen 

navigation channels to the marinas. 

Copper and zinc were elevated at several locations in 

Benner Bay and Mangrove Lagoon. The elevated copper 

level was above the NOAA ERM at one site from the 2010 

targeted sampling, indicating that impacts to benthic organisms and within the broader food web are likely. This also 

appears to be associated with marina activities, including 

the mooring of vessels, along with the cleaning, and scraping of the hulls and subsequent transport of these materials 

into northern Benner Bay. The locations where the three 

highest copper concentrations were found was also the 

location of the three highest TBT concentrations. 

A number of other chemical contaminants analyzed for this 

project, including zinc, lead, copper, mercury, total PCBs, 

and total DDT, were above ERLs at one or more sites in the 

STEER, indicating that impacts may be occurring in some 

of the more sensitive species or life stages that may be present. Additive effects of these levels of contaminants on 

biota in the STEER are possible. Clostridium perfringens, 

a pathogenic bacteria used as sewage indicator, was found 

at high levels in Mangrove Lagoon.

The elevated levels of chemical contaminants in the Mangrove Lagoon and northern Benner Bay areas were refl ected in the results of a number of the toxicity tests. Overall, 

the bioassays indicated a signifi cant gradient (high to low) 

of effects from west to east in the STEER. The widespread 

toxicological responses likely indicate the interaction of 

multiple chemicals, including those beyond the standard 

suite of NS&T analytes, along with other physicochemical 

characteristics which also vary between strata. 

Half of the signifi cant sea urchin fertilization failure bioassays in the STEER were in sediments from Mangrove Lagoon or the canal that joins it to Benner Bay. In addition, 

most of the signifi cant P450 responses were in the western 

strata in the STEER, including all of the Mangrove Lagoon 

sites. The predominant class of contaminants to which the 

cells were responding to appeared to be the PAHs or polycyclic aromatic hydrocarbons, which were elevated in this 

part of the STEER, as opposed to PCBs. 

The benthic infaunal analysis also correlated with the 

chemical contaminant and bioassay data, indicating gradients of diversity and species richness, with lower values 

in the western strata, especially in Mangrove Lagoon, and 

higher values towards the east. Similar to the results of the 

P450 analysis, the number of species and diversity were 

signifi cantly and negatively correlated with benzo[a]pyrene 

concentrations, indicating the likely impacts of this PAH 

and other chemicals present. 

Finally, the nodal analysis showed that the community 

composition of animals in the sediments of Mangrove Lagoon and Benner Bay were distinct in terms of the species 

found from the other three strata in the STEER. Furthermore, the species found in Mangrove Lagoon and Benner 

Bay were for the most part absent from the other strata and 

vice versa, likely due in part to natural and anthropogenic 

stressors found in Mangrove Lagoon and Benner Bay. 

The ecological health and condition of the interconnected 

mangroves, seagrass beds, and coral reefs within the 

STEER are a signifi cant management concern for many, 

including the USVI DPNR and NOAA’s CRCP. The proximity of the Reserves to the Bovoni Landfi ll, marinas, and 

other commercial and industrial activities, combined with 

likely inputs from residential sewer systems, has prompted 

concerns about negative impacts of chemical pollutants on 

natural resources of the STEER. Until this current study, 

very little was known about the types and concentrations of 

chemical contaminants present, or their spatial distribution 

patterns within these Reserves. The information generated 

from this assessment of chemical contaminants, along with 

the bioeffects, establishes a baseline of conditions so that 

managers can understand not only the status, but also the 

challenges that exist to improve the ecological functioning 

of the STEER.

Anthropogenic stressors, concentrated in Benner Bay and 

Mangrove Lagoon, are most likely impacting the ecology 

of the STEER, including the health of juvenile and adult 

species, and likely the spawning of fi sh and invertebrates. 

Loss of suitable habitat further impacts the ability of the 

STEER to be a source of new recruits of marine resource 

species for St. Thomas and beyond. Finally, the STEER 

has so many natural amenities and ecological services to 

offer, it is imperative that they be protected, enhanced, and 

where needed, restored, not only to improve the ecological 

functioning and productivity of the Reserves, but also to 

provide both recreational and economic benefi ts for residents and visitors alike.
STEER Sediment Contaminants and Bioeffects Report

Literature Cited

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STEER Sediment Contaminants and Bioeffects Report

51Appendices

Stratum Site Site Type Date Depth (m) Measured Latitude (DD) Measured Longitude (DD) Surface Temp. (°C ) Bottom Temp. (°C ) Surface Salinity (%) Bottom Salinity (%) Surface DO (mg/L) Bottom DO (mg/L) Secchi Depth (m)

1 1 P 6/15/2011 1.2 18.31538 -64.88128 31.4 31.4 28.32 28.33 7.22 6.31 1.11 2 P 6/15/2011 0.9 18.31499 -64.81677 31.8 N/A 31.46 N/A 6.22 N/A 0.91 3 P 6/15/2011 0.9 18.3159 -64.87617 32.1 32.1 29.15 30.9 6.41 6.74 0.91 4 P 6/15/2011 1.2 18.3089 -64.87443 29.4 28.8 33.14 34.32 5.2 5.27 1.21 5 P 6/15/2011 0.6 18.31477 -64.87476 32.8 N/A 31.62 N/A 8.85 N/A 0.62 16 P 6/14/2011 1.5 18.31672 -64.87375 32.8 32.9 29.11 29.83 5.62 6.49 0.82 19 P 6/14/2011 1.5 18.31389 -64.86786 31.5 30.8 32.91 33.42 5.34 6.15 1.82 20 P 6/14/2011 1.5 18.31849 -64.86726 33.1 N/A 31.05 N/A 5.13 N/A 1.22 24 A 6/14/2011 1.4 18.31379 -64.86827 32.2 31.2 33.03 33.54 6.77 6.55 1.43 32 P 6/14/2011 6.7 18.31693 -64.85516 30.4 29.4 34.38 34.45 5.83 6.56 6.73 33 P 6/16/2011 17.7 18.30513 -64.85267 28.9 28.9 34.35 34.36 5.74 5.75 9.83 37 A 6/17/2011 12.8 18.31039 -64.84875 28.9 28.9 34.46 34.46 5.75 5.76 12.83 38 A 6/17/2011 6.6 18.31735 -64.85635 29.4 29.2 34.44 34.43 5.94 6.18 6.43 45 A 6/17/2011 11.3 18.31228 -64.85199 29.1 29 34.46 34.46 5.82 5.8 11.34 46 P 6/16/2011 16.5 18.30429 -64.83998 28.9 28.8 34.39 34.46 5.66 5.65 9.14 47 P 6/17/2011 9.4 18.30177 -64.83553 28.8 28.7 34.44 34.47 5.77 5.63 9.44 48 P 6/15-16 2011 10.4 18.3125 -64.83687 28.7 28.7 34.46 34.46 5.65 5.61 11.04 49 P 6/17/2011 4.6 18.30413 -64.82621 28.6 28.6 34.5 34.5 5.45 5.53 4.64 50 P 6/15/2011 6.1 18.31525 -64.84118 29.5 29.3 34.47 34.44 5.89 6.1 6.15 61 P 6/16/2011 12.2 18.31725 -64.83537 28.6 28.5 34.52 34.61 5.62 5.42 12.25 62 P 6/16/2011 12.8 18.3179 -64.82919 28.7 28.5 34.49 34.55 5.52 5.56 9.45 70 A 6/16/2011 7.9 18.3225 -64.84019 28.6 28.7 34.41 34.51 4.98 5.42 6.15 71 A 6/16/2011 17.4 18.32100 -64.83443 28.7 28.6 34.47 34.53 5.86 5.64 9.85 75 A 6/16/2011 10.2 18.32246 -64.83707 28.8 28.7 34.49 34.5 5.57 5.58 10.2

Note: DO, dissolved oxygen; lat, latitude; long, longitude; N/A, reading not taken.

Appendix A. Field data collected from the STEER 2011 mission.
52Appendices

STEER Sediment Contaminants and Bioeffects Report

Site Total Organic 

Carbon (%TOC)

Total Inorganic 

Carbon (%TIC) %Gravel %Sand %Silt %Clay

1-1P 2.07 1.33 0.00 34.55 35.55 29.90

1-2P 3.15 8.16 18.95 25.79 31.17 24.09

1-3P 4.26 7.84 8.56 28.64 38.58 24.22

1-4P 1.18 3.91 4.97 84.09 6.25 4.69

1-5P 3.46 7.23 12.41 39.46 29.45 18.68

2-16P 1.92 9.38 17.20 52.21 15.13 15.46

2-19P 1.62 2.64 6.56 84.32 3.58 5.54

2-20P 1.87 7.24 13.14 54.48 23.87 8.51

2-24A 1.79 9.63 15.64 73.87 3.19 7.30

3-32P 1.74 9.19 2.49 58.56 29.76 9.19

3-33P 4.13 7.94 7.23 90.61 2.16 0.00

3-37A 5.44 6.61 9.21 84.76 2.41 3.62

3-38A 2.17 9.28 8.23 82.64 3.18 5.95

3-45A 1.09 9.99 7.58 74.85 13.10 4.47

4-46P 3.05 4.24 2.73 91.11 5.34 0.82

4-47P 5.44 5.74 10.36 85.41 1.32 2.91

4-48P 5.46 6.52 0.00 97.08 0.61 2.31

4-49P 4.82 6.33 32.20 64.79 1.00 2.01

4-50P 0.49 10.16 0.00 95.37 0.93 3.70

5-61P 0.49 10.72 1.05 84.90 9.91 4.14

5-62P 2.13 4.33 8.18 73.08 11.50 7.24

5-70A 1.22 10.54 12.23 53.39 29.34 5.04

5-71A 0.44 10.05 7.12 76.20 13.52 3.16

5-75A 0.46 11.23 7.91 61.93 22.41 7.75

BB-1 3.48 3.54 8.81 34.56 49.02 7.61

BB-2 2.04 2.96 23.97 34.62 35.06 6.35

ML-2 5.18 2.45 0.00 12.36 36.75 50.89

ML-10 3.74 3.35 14.78 49.51 26.55 9.16

TOC, total organic carbon; TIC, total inorganic carbon

Appendix B. Grain size and organic carbon of sediments from St. Thomas East End Reserves.
STEER Sediment Contaminants and Bioeffects Report

53Appendices

Appendix C. PAHs detected in sediments from the St. Thomas East End Reserves (ng/ dry g).

Compound 1-1P 1-2P 1-3P 1-4P 1-5P 2-16P 2-19P 2-20P 2-24A 3-32P 3-33P 3-37A

Naphthalene 7.3 7.3 9.2 0.3 5.3 2.3 0.5 2.0 0.6 0.9 0.3 0.2 

C1-Naphthalenes 5.4 5.3 6.0 0.2 J 4.0 1.8 0.3 J 1.3 0.4 0.4 0.1 J 0.1 J

C2-Naphthalenes 11.3 11.0 11.9 0.6 8.4 2.8 0.8 2.3 0.6 0.7 0.0 U 0.3 J

C3-Naphthalenes 6.6 8.1 9.9 0.0 U 5.7 1.9 0.0 U 2.7 0.0 U 0.8 0.0 U 0.0 U

C4-Naphthalenes 0.0 U 10.9 14.9 0.0 U 6.1 2.5 0.0 U 3.3 0.0 U 1.2 0.0 U 0.0 U

Benzothiophene 0.1 J 0.2 0.2 0.0 U 0.1 J 0.0 J 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

C1-Benzothiophenes 0.0 U 0.6 2.4 0.0 U 0.6 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

C2-Benzothiophenes 0.0 U 1.8 2.5 0.0 U 0.9 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

C3-Benzothiophenes 0.0 U 3.8 2.2 0.0 U 0.4 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

Biphenyl 2.4 2.3 3.6 0.2 1.4 1.3 0.3 0.6 0.2 1.7 I 0.2 0.1 J

Acenaphthylene 0.8 2.2 3.4 0.0 U 0.8 0.9 0.0 J 0.9 0.0 U 0.2 J 0.0 U 0.0 U

Acenaphthene 0.5 0.5 0.7 0.0 U 0.3 0.1 J 0.1 J 0.3 0.0 U 0.2 0.0 U 0.0 U

Dibenzofuran 3.2 3.3 3.2 0.2 2.5 0.9 0.4 0.7 0.3 0.8 0.2 J 0.2 J

Fluorene 2.8 3.3 3.3 0.1 J 2.6 0.8 0.3 0.8 0.2 0.4 0.1 J 0.1 J

C1-Fluorenes 0.0 U 4.4 5.3 0.0 U 2.5 1.5 0.2 J 0.0 U 0.0 U 0.5 0.0 U 0.0 U

C2-Fluorenes 0.0 U 13.1 19.3 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 1.3 0.0 U 0.0 U

C3-Fluorenes 0.0 U 16.5 22.1 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 2.0 0.0 U 0.0 U

Anthracene 1.5 3.2 5.6 0.0 J 1.1 1.5 0.1 J 1.7 0.0 U 1.3 0.0 U 0.0 U

Phenanthrene 8.6 13.7 18.2 0.4 9.5 4.3 1.0 4.4 0.7 11.2 0.3 0.3 

C1-Phenanthrenes/Anthracenes 7.3 15.2 23.8 0.1 J 6.5 5.1 0.0 U 4.9 0.0 U 4.4 0.0 U 0.0 U

C2-Phenanthrenes/Anthracenes 0.0 U 26.4 45.2 0.0 U 9.3 11.2 0.0 U 10.6 0.0 U 4.7 0.0 U 0.0 U

C3-Phenanthrenes/Anthracenes 0.0 U 33.0 55.1 0.0 U 0.0 U 12.2 0.0 U 11.5 0.0 U 1.9 0.0 U 0.0 U

C4-Phenanthrenes/Anthracenes 0.0 U 25.3 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 1.7 0.0 U 0.0 U

Dibenzothiophene 1.6 1.9 2.6 0.1 J 1.3 0.6 0.1 J 0.6 0.1 J 0.6 0.0 U 0.0 U

C1-Dibenzothiophenes 1.6 2.6 3.7 0.0 U 1.4 0.8 0.1 J 0.6 0.1 J 0.4 0.0 U 0.0 U

C2-Dibenzothiophenes 3.3 7.4 11.9 0.0 U 2.7 2.3 0.0 U 1.8 0.0 U 0.6 0.0 U 0.0 U

C3-Dibenzothiophenes 0.0 U 16.4 25.5 0.0 U 0.0 U 5.1 0.0 U 2.9 0.0 U 0.4 0.0 U 0.0 U

Fluoranthene 4.7 17.4 23.6 0.2 J 5.1 6.2 0.3 9.5 0.2 90.0 0.1 J 0.1 J

Pyrene 4.9 20.9 33.8 0.1 J 5.4 7.7 0.3 10.4 0.1 J 70.2 0.1 J 0.1 J

C1-Fluoranthenes/Pyrenes 6.3 17.4 34.9 0.0 U 4.9 13.2 0.4 9.1 0.0 U 17.5 0.0 U 0.0 U

C2-Fluoranthenes/Pyrenes 0.0 U 28.5 53.3 0.0 U 0.0 U 23.4 0.5 11.9 0.0 U 15.7 0.0 U 0.0 U

C3-Fluoranthenes/Pyrenes 0.0 U 22.6 38.6 0.0 U 0.0 U 12.0 0.0 U 4.5 0.0 U 5.3 0.0 U 0.0 U

Naphthobenzothiophene 0.0 U 12.5 41.7 0.0 U 0.0 U 11.7 0.0 U 4.1 0.0 U 19.0 0.0 U 0.0 U

C1-Naphthobenzothiophenes 0.0 U 24.6 48.0 0.0 U 0.0 U 14.6 0.0 U 4.1 0.0 U 6.0 0.0 U 0.0 U

C2-Naphthobenzothiophenes 0.0 U 36.4 53.1 0.0 U 0.0 U 19.2 0.0 U 4.6 0.0 U 3.2 0.0 U 0.0 U

C3-Naphthobenzothiophenes 0.0 U 30.1 40.7 0.0 U 0.0 U 16.5 0.0 U 4.7 0.0 U 2.3 0.0 U 0.0 U

Benz(a)anthracene 3.9 11.4 20.2 0.0 U 2.2 6.2 0.1 J 7.7 0.0 U 49.8 0.0 U 0.0 J

Chrysene/Triphenylene 5.7 20.5 33.0 0.0 U 5.2 6.5 0.2 8.1 0.0 U 52.0 0.0 U 0.1 J

C1-Chrysenes 0.0 U 26.9 50.1 0.0 U 0.0 U 14.3 0.0 U 6.5 0.0 U 13.7 0.0 U 0.0 U

C2-Chrysenes 0.0 U 27.4 40.3 0.0 U 0.0 U 14.5 0.0 U 5.2 0.0 U 5.3 0.0 U 0.0 U

C3-Chrysenes 0.0 U 17.6 25.0 0.0 U 0.0 U 9.8 0.0 U 3.7 0.0 U 1.9 0.0 U 0.0 U

C4-Chrysenes 0.0 U 8.6 10.5 0.0 U 0.0 U 8.5 0.0 U 0.0 U 0.0 U 2.3 0.0 U 0.0 U

Benzo(b)fluoranthene 13.2 43.0 79.1 0.2 J 13.9 19.1 0.4 21.5 0.0 U 54.9 0.0 U 0.1 J

Benzo(k,j)fluoranthene 5.1 9.3 21.0 0.0 J 4.6 6.9 0.1 J 8.1 0.0 U 18.8 0.0 U 0.0 J

Benzo(e)pyrene 7.3 30.1 62.9 0.1 J 9.7 14.1 0.2 J 13.3 0.0 U 26.4 0.0 U 0.1 J

Benzo(a)pyrene 6.9 20.3 34.9 0.1 J 7.0 8.5 0.2 J 10.6 0.0 U 35.1 0.0 U 0.1 J

Perylene 2.0 7.0 13.4 0.1 J 1.9 3.1 0.1 J 2.7 0.0 U 12.4 0.0 U 0.1 J

Indeno(1,2,3-c,d)pyrene 3.7 10.0 18.0 0.1 J 4.8 7.0 0.3 J 9.4 0.0 U 31.8 0.0 U 0.1 J

Dibenzo(a,h)anthracene 1.3 3.4 6.4 0.0 U 1.6 2.1 0.0 J 2.4 0.0 U 8.2 0.0 U 0.0 U

Benzo(g,h,i)perylene 5.8 19.6 36.9 0.2 9.3 14.4 0.5 13.9 0.2 30.7 0.0 U 0.1 J

Total PAHs 135 705 1131 3.2 149 319 7.7 230 3.7 611 1.3 2.3

Individual Alkyl Isomers and Hopanes*

2-Methylnaphthalene 5.4 5.3 6.2 0.1 J 4.0 1.9 0.3 J 1.4 0.4 0.5 0.1 J 0.1 J

1-Methylnaphthalene 2.6 2.5 2.7 0.1 J 2.0 0.7 0.2 J 0.5 0.2 J 0.2 J 0.1 J 0.1 J

2,6-Dimethylnaphthalene 5.5 5.9 6.6 0.5 4.9 1.7 0.6 1.3 0.4 0.6 0.0 U 0.2 J

1,6,7-Trimethylnaphthalene 0.8 1.0 1.2 0.0 U 0.7 0.2 J 0.0 U 0.0 U 0.0 U 0.1 J 0.0 U 0.0 U

1-Methylphenanthrene 1.6 2.8 4.4 0.0 U 0.7 0.6 0.0 U 0.7 0.0 U 1.2 0.0 U 0.0 U

C29-Hopane 805 733 1304 10.3 692 552 26.4 474 9 15 0.0 U 1.3 

18a-Oleanane 87.2 96.4 147 0.0 U 83.1 68.3 0.0 U 55.3 0.0 U 3.3 0.0 U 0.0 U

C30-Hopane 652 562 979 12.9 560 466 27.8 426 9.6 17.1 0.0 U 1.6 

Notes: J, below method detection level, MDL; U, not detected

*Individual isomers contained in alkylated (C1-C4 sums)
54Appendices

STEER Sediment Contaminants and Bioeffects Report

Appendix C. PAHs detected in sediments from the St. Thomas East End Reserves (ng/ dry g) (continued).

Compound 3-38A 3-45A 4-46P 4-47P 4-48P 4-49P 4-50P 5-61P 5-62P 5-70A 5-71A 5-75A

Naphthalene 0.3 0.5 0.4 0.2 0.2 0.2 J 0.2 0.4 0.4 0.5 0.2 0.4 

C1-Naphthalenes 0.0 U 0.2 J 0.2 J 0.1 J 0.1 J 0.1 J 0.1 J 0.2 J 0.2 J 0.3 J 0.2 J 0.2 J

C2-Naphthalenes 0.0 U 0.6 0.5 0.0 U 0.0 U 0.0 U 0.0 U 0.5 0.6 1.0 0.4 0.4 

C3-Naphthalenes 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

C4-Naphthalenes 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

Benzothiophene 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

C1-Benzothiophenes 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

C2-Benzothiophenes 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

C3-Benzothiophenes 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

Biphenyl 0.2 0.2 0.2 0.1 J 0.2 0.1 J 0.1 J 0.2 0.2 0.2 0.2 0.2 

Acenaphthylene 0.0 U 0.0 J 0.0 J 0.0 U 0.0 U 0.0 U 0.1 J 0.0 J 0.0 U 0.0 U 0.0 U 0.0 U

Acenaphthene 0.0 U 0.1 J 0.0 J 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

Dibenzofuran 0.2 0.2 0.3 0.2 J 0.2 0.1 J 0.1 J 0.3 0.3 0.3 0.2 J 0.2 

Fluorene 0.1 J 0.2 J 0.2 J 0.1 J 0.1 J 0.1 J 0.1 J 0.2 J 0.3 0.2 0.1 J 0.2 J

C1-Fluorenes 0.0 U 0.2 J 0.2 J 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

C2-Fluorenes 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

C3-Fluorenes 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

Anthracene 0.1 J 0.1 J 0.0 J 0.0 U 0.0 U 0.0 J 0.1 J 0.0 U 0.2 0.1 J 0.0 J 0.1 J

Phenanthrene 0.8 0.7 0.5 0.2 0.2 0.2 0.3 0.6 1.3 0.9 0.3 0.6 

C1-Phenanthrenes/Anthracenes 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 1.1 1.1 0.0 U 0.0 U

C2-Phenanthrenes/Anthracenes 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

C3-Phenanthrenes/Anthracenes 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

C4-Phenanthrenes/Anthracenes 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

Dibenzothiophene 0.0 U 0.1 J 0.1 J 0.0 U 0.0 J 0.0 U 0.0 U 0.1 J 0.1 J 0.1 J 0.1 J 0.0 U

C1-Dibenzothiophenes 0.0 U 0.0 U 0.1 J 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.1 J 0.0 U 0.0 U 0.0 U

C2-Dibenzothiophenes 0.0 U 0.0 U 0.1 J 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

C3-Dibenzothiophenes 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

Fluoranthene 4.5 1.2 0.1 J 0.0 J 0.1 J 0.1 J 0.2 0.3 1.9 0.5 0.3 0.2 

Pyrene 3.3 0.9 0.1 J 0.0 J 0.0 J 0.0 J 0.2 0.2 1.6 0.3 0.2 0.2 J

C1-Fluoranthenes/Pyrenes 1.0 0.4 J 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.7 0.3 J 0.0 U 0.0 U

C2-Fluoranthenes/Pyrenes 0.9 0.4 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.3 J 0.0 U 0.0 U 0.0 U

C3-Fluoranthenes/Pyrenes 0.2 J 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.2 J 0.0 U 0.0 U 0.0 U

Naphthobenzothiophene 0.0 U 0.2 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.4 0.0 U 0.0 U 0.0 U

C1-Naphthobenzothiophenes 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

C2-Naphthobenzothiophenes 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

C3-Naphthobenzothiophenes 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

Benz(a)anthracene 2.1 0.5 0.0 J 0.0 U 0.0 U 0.0 U 0.2 0.1 1.4 0.2 0.1 J 0.1 J

Chrysene/Triphenylene 3.2 0.8 0.1 J 0.0 U 0.0 J 0.0 U 0.2 0.2 1.5 0.3 0.1 J 0.2 J

C1-Chrysenes 0.8 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.4 0.0 U 0.0 U 0.0 U

C2-Chrysenes 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

C3-Chrysenes 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

C4-Chrysenes 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

Benzo(b)fluoranthene 4.3 1.3 0.1 J 0.0 U 0.0 U 0.0 U 0.4 0.4 2.2 0.4 0.3 J 0.3 J

Benzo(k,j)fluoranthene 1.5 0.4 0.0 J 0.0 U 0.0 U 0.0 U 0.4 0.1 J 0.5 0.1 J 0.1 J 0.1 J

Benzo(e)pyrene 2.4 0.7 0.1 J 0.0 U 0.0 U 0.0 U 0.2 J 0.2 J 1.1 0.3 J 0.1 J 0.1 J

Benzo(a)pyrene 2.5 0.8 0.1 J 0.0 U 0.0 U 0.0 U 0.3 0.2 J 1.8 0.3 0.2 J 0.2 J

Perylene 0.8 J 0.4 J 0.2 J 0.0 U 0.0 U 0.0 U 0.1 J 0.1 J 0.6 J 0.2 J 0.1 J 0.1 J

Indeno(1,2,3-c,d)pyrene 2.1 0.7 0.1 J 0.0 U 0.0 U 0.0 U 0.2 J 0.2 J 1.0 0.3 0.2 J 0.2 J

Dibenzo(a,h)anthracene 0.6 0.2 0.0 U 0.0 U 0.0 U 0.0 U 0.1 J 0.0 U 0.3 0.1 J 0.0 U 0.0 U

Benzo(g,h,i)perylene 2.1 0.7 0.1 J 0.0 U 0.0 U 0.0 U 0.2 0.0 U 1.1 0.5 0.3 0.2 

Total PAHs 33.8 12.8 3.6 1.0 1.2 0.9 3.8 4.3 21.5 8.5 3.7 4.2

Individual Alkyl Isomers and Hopanes*

2-Methylnaphthalene 0.0 U 0.2 J 0.2 J 0.1 J 0.1 J 0.1 J 0.1 J 0.2 J 0.2 J 0.3 J 0.2 J 0.2 J

1-Methylnaphthalene 0.0 U 0.1 J 0.1 J 0.1 J 0.1 J 0.0 J 0.1 J 0.1 J 0.1 J 0.1 J 0.1 J 0.1 J

2,6-Dimethylnaphthalene 0.0 U 0.3 J 0.3 J 0.0 U 0.0 U 0.0 U 0.0 U 0.2 J 0.2 J 0.8 0.3 J 0.3 J

1,6,7-Trimethylnaphthalene 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 J 0.0 U

1-Methylphenanthrene 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.1 J 0.2 J 0.0 U 0.0 U

C29-Hopane 3.4 4.8 2.6 0 U 0.0 U 0.0 U 2.4 3.5 4.7 11 5.1 7.8 

18a-Oleanane 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U 0.0 U

C30-Hopane 4.2 5.7 2.9 0 U 0.0 U 0.0 U 2.7 5.4 6.1 13.8 6.9 9.7 

Notes: J, below method detection level, MDL; U, not detected

*Individual isomers contained in alkylated (C1-C4 sums)
STEER Sediment Contaminants and Bioeffects Report

55Appendices

Appendix C. PAHs detected in sediments from the St. Thomas East End Reserves (ng

Compound BB-1 BB-2 ML-2 ML10

Naphthalene 5.4 6.4 1.9 7.3 

C1-Naphthalenes 3.7 4.7 1.4 4.6 

C2-Naphthalenes 8.1 8.0 5.1 9.2 

C3-Naphthalenes 9.3 8.0 3.4 7.4 

C4-Naphthalenes 15.1 6.9 6.3 11.4 

Benzothiophene 0.0 U 0.0 U 0.0 U 0.2 

C1-Benzothiophenes 0.0 U 0.0 U 0.0 U 5.3 

C2-Benzothiophenes 0.0 U 0.0 U 0.0 U 6.6 

C3-Benzothiophenes 0.0 U 0.0 U 0.0 U 6.6 

Biphenyl 2.5 2.3 1.0 2.1 

Acenaphthylene 2.8 4.0 0.8 2.4 

Acenaphthene 1.1 1.0 1.1 1.2 

Dibenzofuran 3.4 4.2 0.8 3.6 

Fluorene 9.1 9.1 5.3 7.4 

C1-Fluorenes 4.5 6.0 0.0 U 3.4 

C2-Fluorenes 15.7 0.0 U 0.0 U 13.3 

C3-Fluorenes 26.4 0.0 U 0.0 U 24.2 

Anthracene 7.4 9.2 1.7 5.7 

Phenanthrene 33.9 31.7 5.0 30.6 

C1-Phenanthrenes/Anthracenes 17.1 16.9 6.1 19.0 

C2-Phenanthrenes/Anthracenes 46.1 36.9 19.4 46.8 

C3-Phenanthrenes/Anthracenes 49.4 30.1 0.0 U 56.0 

C4-Phenanthrenes/Anthracenes 0.0 U 0.0 U 0.0 U 30.0 

Dibenzothiophene 2.7 2.6 0.8 3.1 

C1-Dibenzothiophenes 2.5 2.2 1.7 2.2 

C2-Dibenzothiophenes 6.8 7.5 0.0 U 9.3 

C3-Dibenzothiophenes 10.0 12.3 0.0 U 24.9 

Fluoranthene 17.3 19.3 6.8 33.7 

Pyrene 19.3 22.7 6.8 38.8 

C1-Fluoranthenes/Pyrenes 23.1 25.3 9.8 37.4 

C2-Fluoranthenes/Pyrenes 52.0 28.8 113.0 121.0 

C3-Fluoranthenes/Pyrenes 28.9 14.4 17.3 80.8 

Naphthobenzothiophene 0.0 U 0.0 U 0.0 U 0.0 U

C1-Naphthobenzothiophenes 0.0 U 0.0 U 0.0 U 0.0 U

C2-Naphthobenzothiophenes 0.0 U 0.0 U 0.0 U 0.0 U

C3-Naphthobenzothiophenes 0.0 U 0.0 U 0.0 U 0.0 U

Benz(a)anthracene 12.0 16.0 5.6 33.9 

Chrysene/Triphenylene 10.9 14.5 6.3 27.5 

C1-Chrysenes 15.1 18.3 7.9 30.8 

C2-Chrysenes 20.1 20.1 15.4 53.1 

C3-Chrysenes 8.6 9.0 7.8 41.1 

C4-Chrysenes 0.0 U 0.0 U 0.0 U 0.0 U

Benzo(b)fluoranthene 17.9 39.0 6.1 24.6 

Benzo(k,j)fluoranthene 5.4 7.3 2.0 7.1 

Benzo(e)pyrene 9.3 16.0 2.9 15.5 

Benzo(a)pyrene 9.6 17.5 3.3 15.6 

Perylene 5.7 5.0 3.9 9.5 

Indeno(1,2,3-c,d)pyrene 8.4 16.6 3.1 9.6 

Dibenzo(a,h)anthracene 7.4 6.9 6.8 11.6 

Benzo(g,h,i)perylene 11.8 24.5 3.7 15.1 

Total PAHs 566 531 290 951

Individual Alkyl Isomers and Hopanes*

2-Methylnaphthalene 3.9 5.0 1.4 4.9 

1-Methylnaphthalene 1.8 2.2 0.7 2.2 

2,6-Dimethylnaphthalene 4.1 4.2 3.6 5.1 

1,6,7-Trimethylnaphthalene 0.9 0.8 0.4 0.7 

1-Methylphenanthrene 3.5 7.6 1.4 3.8 

C29-Hopane 337 493 365 364 

18a-Oleanane 0.0 U 0.0 U 0.0 U 0.0 U

C30-Hopane 106 428 315 289 

Notes: J, below method detection level, MDL; U, not detected

*Individual isomers contained in alkylated (C1-C4 sums)
56Appendices

STEER Sediment Contaminants and Bioeffects Report

Compound 1-1P 1-2P 1-3P 1-4P 1-5P 2-16P 2-19P 2-20P 2-24A 3-32P 

n-C9 0.000 U 0.000 U 0.000 U 0.010 J 0.000 U 0.000 U 0.012 J 0.000 U 0.016 0.000 U

n-C10 0.000 U 0.000 U 0.000 U 0.006 J 0.000 U 0.000 U 0.008 J 0.000 U 0.005 J 0.000 U

n-C11 0.000 U 0.000 U 0.000 U 0.002 J 0.000 U 0.000 U 0.004 J 0.000 U 0.005 J 0.000 U

n-C12 0.000 U 0.000 U 0.000 U 0.015 J 0.000 U 0.000 U 0.014 J 0.000 U 0.007 J 0.012 J

n-C13 0.000 U 0.000 U 0.000 U 0.005 J 0.000 U 0.000 U 0.005 J 0.000 U 0.004 J 0.002 J

i-C15 0.000 U 0.000 U 0.000 U 0.002 J 0.000 U 0.000 U 0.001 J 0.000 U 0.000 U 0.000 U

n-C14 0.000 U 0.000 U 0.000 U 0.014 0.000 U 0.000 U 0.016 0.000 U 0.005 J 0.009 J

i-C16 0.000 U 0.000 U 0.000 U 0.002 J 0.000 U 0.000 U 0.002 J 0.000 U 0.002 J 0.015

n-C15 0.000 U 0.000 U 0.000 U 0.038 0.000 U 0.000 U 0.017 0.000 U 0.007 J 0.029

n-C16 0.000 U 0.000 U 0.000 U 0.010 0.000 U 0.000 U 0.011 0.000 U 0.007 0.018

i-C18 0.000 U 0.000 U 0.000 U 0.004 0.000 U 0.000 U 0.002 J 0.000 U 0.000 U 0.000 U

n-C17 0.000 U 0.000 U 0.000 U 0.141 0.000 U 0.000 U 0.108 0.000 U 0.021 0.097

Pristane 0.000 U 0.000 U 0.000 U 0.006 0.000 U 0.000 U 0.012 0.000 U 0.005 0.010

n-C18 0.000 U 0.000 U 0.000 U 0.023 0.000 U 0.000 U 0.032 0.000 U 0.030 0.071

Phytane 0.000 U 0.000 U 0.000 U 0.006 0.000 U 0.000 U 0.006 0.000 U 0.005 J 0.040

n-C19 0.000 U 0.000 U 0.000 U 0.021 0.000 U 0.000 U 0.023 0.000 U 0.013 0.050

n-C20 0.000 U 0.000 U 0.000 U 0.013 0.000 U 0.000 U 0.023 0.000 U 0.011 J 0.014

n-C21 0.000 U 0.000 U 0.000 U 0.015 0.000 U 0.000 U 0.019 0.000 U 0.007 0.057

n-C22 0.000 U 0.000 U 0.000 U 0.009 0.000 U 0.000 U 0.008 0.000 U 0.004 0.024

n-C23 0.000 U 0.000 U 0.000 U 0.011 0.000 U 0.000 U 0.014 0.000 U 0.009 0.203

n-C24 0.000 U 0.000 U 0.000 U 0.005 0.000 U 0.000 U 0.004 J 0.000 U 0.005 0.021

n-C25 0.000 U 0.000 U 0.000 U 0.032 0.000 U 0.000 U 0.023 0.000 U 0.015 0.247

n-C26 0.000 U 0.000 U 0.000 U 0.011 0.000 U 0.000 U 0.005 J 0.000 U 0.005 J 0.011

n-C27 0.000 U 0.000 U 0.000 U 0.023 0.000 U 0.000 U 0.012 0.000 U 0.006 J 1.793

n-C28 0.000 U 0.000 U 0.000 U 0.021 0.000 U 0.000 U 0.011 J 0.000 U 0.009 J 0.056

n-C29 0.000 U 0.000 U 0.000 U 0.075 0.000 U 0.000 U 0.036 0.000 U 0.031 0.268

n-C30 0.000 U 0.000 U 0.000 U 0.009 J 0.000 U 0.000 U 0.007 J 0.000 U 0.008 J 0.027

n-C31 0.000 U 0.000 U 0.000 U 0.069 0.000 U 0.000 U 0.052 0.000 U 0.010 J 0.183

n-C32 0.000 U 0.000 U 0.000 U 0.010 J 0.000 U 0.000 U 0.003 J 0.000 U 0.000 U 0.041

n-C33 0.000 U 0.000 U 0.000 U 0.116 0.000 U 0.000 U 0.044 0.000 U 0.000 U 0.085

n-C34 0.000 U 0.000 U 0.000 U 0.013 J 0.000 U 0.000 U 0.005 J 0.000 U 0.000 U 0.027

n-C35 0.000 U 0.000 U 0.000 U 0.034 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.035

n-C36 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.026

n-C37 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.090

n-C38 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.055

n-C39 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.057

n-C40 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U

TEH 753 733 1,104 48.0 482 309 30.7 300 1.41 41.5

Notes: J, below method detection level, MDL; U, not detected

Appendix D. Aliphatics and total extractable hydrocarbons from the St. Th omas East End Reserves.
STEER Sediment Contaminants and Bioeffects Report

57Appendices

Compound 3-33P 3-37A 3-38A 3-45A 4-46P 4-47P 4-48P 4-49P 4-50P 5-61P

n-C9 0.000 U 0.015 0.000 U 0.016 0.015 0.017 0.000 U 0.014 0.011 J 0.013

n-C10 0.000 U 0.003 J 0.000 U 0.007 J 0.006 J 0.003 J 0.000 U 0.003 J 0.004 J 0.005 J

n-C11 0.000 U 0.002 J 0.000 U 0.002 J 0.003 J 0.002 J 0.000 U 0.001 J 0.002 J 0.001 J

n-C12 0.000 U 0.006 J 0.000 U 0.015 J 0.009 J 0.008 J 0.000 U 0.007 J 0.010 J 0.010 J

n-C13 0.000 U 0.005 J 0.000 U 0.005 J 0.005 J 0.005 J 0.000 U 0.004 J 0.004 J 0.006 J

i-C15 0.000 U 0.000 U 0.000 U 0.001 J 0.001 J 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U

n-C14 0.000 U 0.004 J 0.000 U 0.016 0.010 J 0.007 J 0.000 U 0.005 J 0.009 J 0.010 J

i-C16 0.000 U 0.000 U 0.000 U 0.002 J 0.001 J 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U

n-C15 0.000 U 0.012 J 0.000 U 0.027 0.012 J 0.016 J 0.000 U 0.028 0.011 J 0.010 J

n-C16 0.000 U 0.004 J 0.000 U 0.011 0.007 0.008 0.000 U 0.009 0.006 0.008

i-C18 0.000 U 0.000 U 0.000 U 0.005 0.002 J 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U

n-C17 0.000 U 0.072 0.000 U 0.116 0.029 0.073 0.000 U 0.186 0.027 0.022

Pristane 0.000 U 0.003 0.000 U 0.009 0.002 J 0.001 J 0.000 U 0.002 J 0.001 J 0.002 J

n-C18 0.000 U 0.004 0.000 U 0.032 0.003 J 0.017 0.000 U 0.025 0.012 0.019

Phytane 0.000 U 0.002 J 0.000 U 0.008 0.002 J 0.004 J 0.000 U 0.004 J 0.004 J 0.006

n-C19 0.000 U 0.008 0.000 U 0.034 0.015 0.015 0.000 U 0.018 0.011 0.017

n-C20 0.000 U 0.009 J 0.000 U 0.008 J 0.006 J 0.013 0.000 U 0.019 0.003 J 0.007 J

n-C21 0.000 U 0.007 0.000 U 0.026 0.017 0.016 0.000 U 0.005 0.016 0.023

n-C22 0.000 U 0.000 U 0.000 U 0.013 0.005 0.005 0.000 U 0.003 J 0.006 0.008

n-C23 0.000 U 0.000 U 0.000 U 0.070 0.035 0.014 0.000 U 0.006 J 0.030 0.072

n-C24 0.000 U 0.000 U 0.000 U 0.007 0.005 J 0.005 0.000 U 0.006 0.006 0.008

n-C25 0.000 U 0.000 U 0.000 U 0.092 0.030 0.026 0.000 U 0.008 0.037 0.105

n-C26 0.000 U 0.000 U 0.000 U 0.004 J 0.007 J 0.004 J 0.000 U 0.004 J 0.004 J 0.008

n-C27 0.000 U 0.000 U 0.000 U 0.028 0.009 J 0.006 J 0.000 U 0.003 J 0.016 0.041

n-C28 0.000 U 0.000 U 0.000 U 0.009 J 0.006 J 0.005 J 0.000 U 0.003 J 0.004 J 0.006 J

n-C29 0.000 U 0.000 U 0.000 U 0.049 0.012 J 0.009 J 0.000 U 0.000 U 0.013 J 0.046

n-C30 0.000 U 0.000 U 0.000 U 0.011 J 0.005 J 0.003 J 0.000 U 0.000 U 0.004 J 0.004 J

n-C31 0.000 U 0.000 U 0.000 U 0.055 0.017 0.004 J 0.000 U 0.000 U 0.014 J 0.036

n-C32 0.000 U 0.000 U 0.000 U 0.004 J 0.001 J 0.002 J 0.000 U 0.000 U 0.001 J 0.001 J

n-C33 0.000 U 0.000 U 0.000 U 0.055 0.007 J 0.028 0.000 U 0.000 U 0.022 0.022

n-C34 0.000 U 0.000 U 0.000 U 0.005 J 0.000 U 0.016 J 0.000 U 0.000 U 0.000 U 0.001 J

n-C35 0.000 U 0.000 U 0.000 U 0.018 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U

n-C36 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U

n-C37 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U

n-C38 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U

n-C39 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U

n-C40 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U 0.000 U

TEH 24.0 3.21 22.2 16.4 6.36 2.57 31.6 2.06 23.0 16.8

Notes: J, below method detection level, MDL; U, not detected

Appendix D. Aliphatics and total extractable hydrocarbons from the St. Thomas East End Reserves. (continued)
58Appendices

STEER Sediment Contaminants and Bioeffects Report

Appendix D. Aliphatics and total extractable hydrocarbons from the St. Th omas East End Reserves. (continued).

Compound 5-62P 5-70A 5-71A 5-75A

n-C9 0.015 0.017 0.010 J 0.015

n-C10 0.009 J 0.003 J 0.005 J 0.005 J

n-C11 0.003 J 0.002 J 0.002 J 0.002 J

n-C12 0.015 J 0.009 J 0.009 J 0.011 J

n-C13 0.004 J 0.006 J 0.006 J 0.004 J

i-C15 0.003 J 0.000 U 0.000 U 0.001 J

n-C14 0.019 0.007 J 0.009 J 0.012 J

i-C16 0.003 J 0.003 J 0.000 U 0.002 J

n-C15 0.019 0.031 0.013 J 0.019

n-C16 0.010 0.017 0.007 0.009 

i-C18 0.003 J 0.000 U 0.000 U 0.002 J

n-C17 0.064 0.474 0.182 0.071

Pristane 0.005 0.007 0.003 0.002 J

n-C18 0.005 0.050 0.016 0.005

Phytane 0.003 J 0.004 J 0.005 J 0.007

n-C19 0.023 0.061 0.018 0.028

n-C20 0.006 J 0.052 0.003 J 0.003 J

n-C21 0.041 0.049 0.010 0.033

n-C22 0.010 0.009 0.005 0.009

n-C23 0.093 0.124 0.012 0.085

n-C24 0.009 0.008 0.005 J 0.008

n-C25 0.068 0.088 0.037 0.052

n-C26 0.012 0.007 J 0.005 J 0.011

n-C27 0.022 0.466 0.008 J 0.010 J

n-C28 0.009 J 0.018 0.006 J 0.011 J

n-C29 0.027 0.064 0.015 J 0.022

n-C30 0.005 J 0.008 J 0.005 J 0.004 J

n-C31 0.037 0.104 0.017 0.052

n-C32 0.005 J 0.010 J 0.007 J 0.004 J

n-C33 0.027 0.110 0.029 0.069

n-C34 0.000 U 0.029 0.000 U 0.008 J

n-C35 0.000 U 0.033 0.000 U 0.021

n-C36 0.000 U 0.000 U 0.000 U 0.000 U

n-C37 0.000 U 0.000 U 0.000 U 0.000 U

n-C38 0.000 U 0.000 U 0.000 U 0.000 U

n-C39 0.000 U 0.000 U 0.000 U 0.000 U

n-C40 0.000 U 0.000 U 0.000 U 0.000 U

TEH 9.33 4.16 25.1 15.8

Notes: J, below method detection level, MDL; U, not detected
STEER Sediment Contaminants and Bioeffects Report

59Appendices

Appendix E. PCBs detected in the sediments from the St. Thomas East End Reserves.

Compound 1-1P 1-2P 1-3P 1-4P 1-5P 2-16P 2-19P 2-20P 2-24A 3-32P

PCB8/5 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB18 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.04 J 0.00 U 0.00 U 0.00 U 0.00 U

PCB28 0.00 U 0.95 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB29 0.00 U 0.00 U 0.00 U 0.02 J 0.00 U 0.00 U 0.00 U 0.00 U 0.00 J 0.00 U

PCB31 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB44 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB45 0.00 U 0.00 U 0.00 U 0.02 J 0.00 U 0.06 J 0.01 J 0.04 J 0.00 U 0.00 U

PCB49 0.14 0.14 0.00 U 0.00 U 0.16 0.32 0.00 U 0.34 0.00 U 0.00 U

PCB52 0.00 U 0.00 U 0.00 U 0.03 J 0.00 U 0.00 U 0.02 J 0.33 0.00 U 0.00 U

PCB56/60 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.14 0.08 0.24 0.00 U 0.00 U

PCB66 0.00 U 0.16 0.00 U 0.00 U 0.14 0.30 0.00 U 0.43 0.01 J 0.00 U

PCB70 0.00 U 0.19 0.00 U 0.00 U 0.16 0.21 0.09 0.46 0.02 J 0.00 U

PCB74/61 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.08 0.00 U 0.00 U 0.00 U 0.00 U

PCB87/115 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.10 0.00 U 0.00 U

PCB95 0.00 U 0.00 U 0.00 U 0.02 J 0.00 U 0.16 0.08 0.22 0.01 J 0.00 U

PCB99 0.00 U 0.00 U 0.00 U 0.00 U 0.07 0.38 0.00 U 0.82 0.00 U 0.00 U

PCB101/90 0.00 U 0.00 U 0.00 U 0.04 J 0.00 U 0.25 0.06 0.84 0.07 0.00 U

PCB105 0.00 U 0.00 U 0.56 0.00 U 0.00 U 0.10 0.00 U 0.21 0.00 U 0.00 U

PCB110/77 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.12 0.00 U 0.43 0.00 U 0.00 U

PCB118 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.62 0.00 U 0.00 U

PCB128 0.11 0.22 0.35 0.00 U 0.21 0.00 U 0.00 U 0.13 0.00 U 0.00 U

PCB138/160 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.08 J 0.94 0.00 U 0.00 U

PCB146 0.00 U 0.00 U 0.00 U 0.06 J 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB149/123 0.00 U 0.00 U 0.00 U 0.00 U 0.10 0.20 0.00 U 0.40 0.00 U 0.00 U

PCB151 0.11 0.00 U 0.00 U 0.00 U 0.08 J 0.05 J 0.00 U 0.25 0.00 U 0.00 U

PCB153/132 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.01 J 0.00 U

PCB156/171/202 0.00 U 0.00 U 0.00 U 0.01 J 0.00 U 0.00 U 0.02 J 0.00 U 0.00 U 0.00 U

PCB158 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.05 J 0.00 U 0.00 U

PCB170/190 2.08 0.00 U 0.00 U 0.00 U 1.89 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB174 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.06 0.00 U 0.00 U

PCB180 0.11 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.05 0.00 U 0.02 J 0.00 U

PCB183 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.17 0.00 U 0.00 U

PCB187 0.02 J 0.11 0.18 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB194 0.00 U 0.05 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB195/208 0.00 U 0.08 0.00 U 0.00 U 0.00 U 0.00 U 0.03 J 0.00 U 0.00 U 0.00 U

PCB199 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB201/157/173 0.06 0.13 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB206 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB209 0.06 0.00 U 0.00 U 0.00 U 0.07 0.11 0.05 J 0.17 0.00 U 0.00 U

Total PCBs 2.69 2.01 1.09 0.19 2.88 2.50 0.58 7.23 0.14 0.00

Notes: PCB, polychlorinated biphenyl; J, below method detection level, MDL; U, not detected
60Appendices

STEER Sediment Contaminants and Bioeffects Report

Appendix E. PCBs detected in the sediments from the St. Thomas East End Reserves. (continued)

Compound 3-33P 3-37A 3-38A 3-45A 4-46P 4-47P 4-48P 4-49P 4-50P 5-61P

PCB8/5 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB18 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.10 0.00 U

PCB28 0.00 U 0.00 U 0.08 0.00 U 0.00 U 0.08 0.00 U 0.00 U 0.04 J 0.00 U

PCB29 0.01 J 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB31 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.13 0.00 U 0.00 U 0.00 U 0.00 U

PCB44 0.00 U 0.00 U 0.14 0.00 U 0.15 0.15 0.16 0.00 U 0.00 U 0.17

PCB45 0.00 J 0.00 U 0.01 J 0.02 J 0.01 J 0.05 J 0.00 U 0.00 U 0.00 U 0.00 U

PCB49 0.00 U 0.02 J 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB52 0.00 J 0.01 J 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.01 J 0.00 U

PCB56/60 0.00 U 0.00 U 0.08 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB66 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.02 J 0.00 U 0.00 U 0.00 U 0.00 U

PCB70 0.00 U 0.00 U 0.00 U 0.07 0.00 U 0.00 U 0.05 J 0.00 U 0.00 U 0.00 U

PCB74/61 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB87/115 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.01 J

PCB95 0.01 J 0.00 U 0.03 J 0.00 U 0.00 U 0.02 J 0.02 J 0.00 U 0.01 J 0.02 J

PCB99 0.00 U 0.00 U 0.00 U 0.02 J 0.00 U 0.00 U 0.00 U 0.00 U 0.01 J 0.00 U

PCB101/90 0.04 J 0.08 0.14 0.11 0.03 J 0.02 J 0.05 0.03 J 0.00 U 0.00 U

PCB105 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB110/77 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB118 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB128 0.00 U 0.01 J 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB138/160 0.00 U 0.00 U 0.14 0.03 J 0.04 J 0.00 U 0.05 J 0.00 U 0.05 J 0.00 U

PCB146 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB149/123 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB151 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB153/132 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB156/171/202 0.01 J 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.01 J 0.00 U 0.00 U 0.00 U

PCB158 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB170/190 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB174 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB180 0.02 J 0.03 J 0.04 J 0.10 0.00 U 0.00 U 0.01 J 0.00 U 0.01 J 0.03 J

PCB183 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB187 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB194 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB195/208 0.00 U 0.00 U 0.02 J 0.00 U 0.00 U 0.00 U 0.00 J 0.05 0.00 U 0.00 U

PCB199 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB201/157/173 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB206 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB209 0.05 J 0.00 U 0.00 U 0.00 U 0.07 0.00 U 0.00 U 0.00 U 0.11 0.03 J

Total PCBs 0.13 0.15 0.66 0.35 0.30 0.46 0.34 0.08 0.33 0.25

Notes: PCB, polychlorinated biphenyl; J, below method detection level, MDL; U, not detected
STEER Sediment Contaminants and Bioeffects Report

61Appendices

Appendix E. PCBs detected in the sediments from the St. Thomas East End Reserves. (continued)

Compound 5-62P 5-70A 5-71A 5-75A BB-1 BB-2 ML-2 ML-10

PCB8/5 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.46 0.00 U 0.20

PCB18 0.00 U 0.00 U 0.12 0.00 U 0.00 U 0.26 0.00 U 0.08

PCB28 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 3.71 0.85

PCB29 0.00 U 0.00 U 0.02 J 0.00 U 0.00 U 0.00 U 0.06 J 0.00 U

PCB31 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

PCB44 0.15 0.13 0.17 0.00 U 0.28 0.71 0.18 0.28

PCB45 0.01 J 0.00 U 0.00 J 0.00 U 0.00 U 0.07 J 0.09 0.00 U

PCB49 0.00 U 0.00 U 0.00 U 0.00 U 0.89 1.86 0.09 0.13

PCB52 0.00 U 0.01 J 0.00 U 0.00 U 0.93 1.77 0.22 3.03

PCB56/60 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.69 0.00 U 0.17

PCB66 0.00 U 0.00 U 0.00 U 0.00 U 0.41 2.27 0.13 0.22

PCB70 0.00 U 0.12 0.05 J 0.00 U 0.51 1.27 0.05 J 0.16

PCB74/61 0.00 U 0.00 U 0.00 U 0.00 U 0.17 0.56 0.05 J 0.45

PCB87/115 0.05 J 0.00 U 0.00 U 0.00 U 0.21 0.84 0.00 U 0.11

PCB95 0.04 J 0.00 U 0.03 J 0.07 0.36 1.64 0.08 0.18

PCB99 0.02 J 0.00 U 0.00 U 0.00 U 0.70 3.06 0.14 0.26

PCB101/90 0.00 U 0.04 J 0.02 J 0.04 J 0.77 3.63 0.12 0.34

PCB105 0.00 U 0.00 U 0.00 U 0.00 U 0.18 0.90 0.05 0.08

PCB110/77 0.00 U 0.00 U 0.00 U 0.00 U 0.52 3.11 0.11 0.42

PCB118 0.00 U 0.00 U 0.00 U 0.00 U 0.67 3.11 0.20 0.29

PCB128 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 1.18 0.03 J 0.08

PCB138/160 0.04 J 0.00 U 0.06 J 0.13 0.98 5.89 0.36 0.49

PCB146 0.00 U 0.00 U 0.00 U 0.03 J 0.00 U 0.79 0.04 J 0.13

PCB149/123 0.00 U 0.00 U 0.00 U 0.00 U 0.69 2.44 0.21 0.24

PCB151 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.59 0.00 U 0.15

PCB153/132 0.00 U 0.02 J 0.01 J 0.00 U 1.59 7.78 0.42 0.63

PCB156/171/202 0.00 U 0.00 U 0.00 U 0.00 U 0.14 0.60 0.02 J 0.35

PCB158 0.00 U 0.00 U 0.00 U 0.00 U 0.06 J 0.42 0.05 J 0.04 J

PCB170/190 0.00 U 0.00 U 0.00 U 0.00 U 7.39 I 12.59 I 1.88 I 10.04 I

PCB174 0.00 U 0.00 U 0.00 U 0.00 U 0.13 0.68 0.03 J 0.00 U

PCB180 0.00 U 0.00 U 0.02 J 0.04 J 0.82 2.46 0.22 0.70

PCB183 0.00 U 0.00 U 0.00 U 0.00 U 0.11 0.57 0.05 0.04 J

PCB187 0.02 J 0.00 U 0.00 U 0.00 U 0.57 1.65 0.20 0.21

PCB194 0.00 U 0.00 U 0.00 U 0.00 U 0.17 0.88 0.10 0.30

PCB195/208 0.03 J 0.00 U 0.00 U 0.00 U 0.00 U 0.21 0.01 J 0.16

PCB199 0.00 U 0.00 U 0.00 U 0.00 U 0.17 0.49 0.00 U 0.00 U

PCB201/157/173 0.00 U 0.00 U 0.00 U 0.00 U 0.11 0.19 0.04 J 0.29

PCB206 0.00 U 0.00 U 0.00 U 0.00 U 0.08 0.00 U 0.04 J 0.09

PCB209 0.06 0.00 U 0.04 J 0.09 0.27 0.35 0.03 J 0.57

Total PCBs 0.40 0.32 0.53 0.39 19.89 65.94 8.97 21.78

Notes: PCB, polychlorinated biphenyl; J, below method detection level, MDL; U, not detected
62Appendices

STEER Sediment Contaminants and Bioeffects Report

Appendix F. Organochlorine compounds detected in sediments from the St. Thomas East End Reserves (ng/dry g).

Compound 1-1P 1-2P 1-3P 1-4P 1-5P 2-16P 2-19P 2-20P 2-24A 3-32P

Aldrin 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Dieldrin 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Endrin 0.00 U 0.00 U 0.00 U 0.00 U 0.18 0.13 0.00 U 0.28 0.00 U 0.00 U

Heptachlor 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Heptachlor-Epoxide 0.00 U 0.04 J 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Oxychlordane 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Alpha-Chlordane 0.00 U 0.00 U 0.00 U 0.03 J 0.07 0.13 0.00 U 0.00 U 0.00 J 0.00 U

Gamma-Chlordane 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.05 J 0.00 U 0.02 J 0.00 U 0.00 U

Trans-Nonachlor 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.09 0.00 U 0.00 U 0.00 U 0.00 U

Cis-Nonachlor 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.06 0.00 U 0.05 0.00 U 0.00 U

Alpha-HCH 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Beta-HCH 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Delta-HCH 0.00 U 0.00 U 0.00 U 0.01 J 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Gamma-HCH 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

DDMU 0.00 U 0.00 U 0.00 U 0.00 U 0.04 J 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

2,4'-DDD 0.09 0.00 U 0.00 U 0.00 U 0.00 U 0.08 0.00 U 0.26 0.01 J 0.00 U

4,4'-DDD 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.01 J 0.09 0.01 J 0.00 U

2,4'-DDE 0.00 U 0.04 J 0.00 U 0.00 U 0.06 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

4,4'-DDE 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.08 0.00 U 0.00 U

2,4'-DDT 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

4,4'-DDT 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.18 0.00 U 0.00 U

1,2,3,4-Tetrachlorobenzene 0.00 U 0.11 0.00 U 0.00 U 0.00 U 0.00 U 0.03 J 0.11 0.00 U 0.00 U

1,2,4,5-Tetrachlorobenzene 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Hexachlorobenzene 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.16 0.00 U 0.00 U 0.00 U 0.00 U

Pentachloroanisole 0.35 0.37 0.46 0.02 J 0.24 0.00 U 0.02 J 0.14 0.00 U 0.00 U

Pentachlorobenzene 0.05 J 0.09 0.22 0.00 U 0.07 J 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Endosulfan II 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Endosulfan I 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Endosulfan Sulfate 0.06 0.04 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.14 0.00 U 0.00 U

Mirex 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Chlorpyrifos 0.00 U 0.35 0.00 U 0.22 0.00 U 0.25 0.00 U 0.00 U 0.00 U 0.00 U

Total DDT 0.09 0.04 0.00 0.00 0.10 0.08 0.01 0.61 0.02 0.00

Notes: J, below method detection level, MDL; U, not detected
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63Appendices

Appendix F. Organochlorine compounds detected in sediments from the St. Thomas East End Reserves (ng/dry g). (continued)

Compound 3-33P 3-37A 3-38A 3-45A 4-46P 4-47P 4-48P 4-49P 4-50P 5-61P

Aldrin 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Dieldrin 0.00 U 0.00 U 0.00 U 0.00 U 0.10 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Endrin 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Heptachlor 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Heptachlor-Epoxide 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Oxychlordane 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Alpha-Chlordane 0.01 J 0.00 U 0.01 J 0.07 0.00 U 0.01 J 0.01 J 0.01 J 0.01 J 0.02 J

Gamma-Chlordane 0.00 U 0.00 U 0.03 J 0.02 J 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Trans-Nonachlor 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Cis-Nonachlor 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Alpha-HCH 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Beta-HCH 0.00 U 0.03 J 0.00 U 0.12 0.00 U 0.01 J 0.03 J 0.00 U 0.00 U 0.02 J

Delta-HCH 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Gamma-HCH 0.00 U 0.02 J 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.02 J 0.00 U 0.00 U

DDMU 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

2,4'-DDD 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

4,4'-DDD 0.00 J 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 J 0.00 U 0.00 U 0.00 U

2,4'-DDE 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

4,4'-DDE 0.00 U 0.00 U 0.00 U 0.01 J 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

2,4'-DDT 0.00 U 0.00 U 0.00 U 0.08 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

4,4'-DDT 0.02 J 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.04 J 0.00 U 0.00 U 0.00 U

1,2,3,4-Tetrachlorobenzene 0.00 U 0.02 J 0.00 U 0.00 U 0.02 J 0.03 J 0.03 J 0.01 J 0.00 U 0.00 U

1,2,4,5-Tetrachlorobenzene 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Hexachlorobenzene 0.01 J 0.00 U 0.00 U 0.00 U 0.00 U 0.44 0.12 0.00 U 0.00 U 0.00 U

Pentachloroanisole 0.00 U 0.00 U 0.02 J 0.02 J 0.02 J 0.00 U 0.01 J 0.00 U 0.02 J 0.00 U

Pentachlorobenzene 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Endosulfan II 0.00 U 0.00 U 0.01 J 0.00 U 0.01 J 0.00 U 0.00 J 0.00 U 0.00 U 0.01 J

Endosulfan I 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Endosulfan Sulfate 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.01 J 0.00 U 0.00 U

Mirex 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Chlorpyrifos 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Total DDT 0.03 0.00 0.00 0.09 0.00 0.00 0.04 0.00 0.00 0.00

Notes: J, below method detection level, MDL; U, not detected
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Appendix F. Organochlorine compounds detected in sediments from the St. Thomas East End Reserves (ng/dry g). (continued)

Compound 5-62P 5-70A 5-71A 5-75A BB-1 BB-2 ML-2 ML-10

Aldrin 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.96 0.20 0.64

Dieldrin 0.00 U 0.00 U 0.00 U 0.00 U 0.08 0.08 0.05 J 0.07

Endrin 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.38 0.33

Heptachlor 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.20 0.00 U 0.00 U

Heptachlor-Epoxide 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Oxychlordane 0.01 J 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Alpha-Chlordane 0.04 J 0.03 J 0.01 J 0.02 J 0.22 0.09 0.09 0.54

Gamma-Chlordane 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.11 0.01 J 0.31

Trans-Nonachlor 0.00 U 0.00 U 0.00 U 0.00 U 0.09 0.09 0.02 J 0.43

Cis-Nonachlor 0.00 U 0.00 U 0.00 J 0.00 U 0.00 U 0.21 0.08 0.26

Alpha-HCH 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.11

Beta-HCH 0.02 J 0.00 U 0.03 J 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Delta-HCH 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Gamma-HCH 0.00 U 0.05 0.00 U 0.00 U 0.00 U 0.16 0.60 0.31

DDMU 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 1.19 0.06 J 0.42

2,4'-DDD 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.88 0.00 U 0.00 U

4,4'-DDD 0.00 U 0.00 U 0.00 U 0.01 J 0.00 U 0.78 0.05 J 0.12

2,4'-DDE 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

4,4'-DDE 0.00 U 0.00 U 0.00 J 0.00 U 0.30 0.31 0.12 0.26

2,4'-DDT 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.17 0.16 0.00 U

4,4'-DDT 0.00 U 0.00 U 0.00 U 0.00 U 1.01 0.29 0.10 0.07

1,2,3,4-Tetrachlorobenzene 0.00 U 0.00 U 0.01 J 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

1,2,4,5-Tetrachlorobenzene 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Hexachlorobenzene 0.00 U 0.00 U 0.00 U 0.00 U 0.10 0.14 0.00 U 0.08

Pentachloroanisole 0.00 U 0.00 U 0.02 J 0.03 J 0.25 0.16 0.12 0.16

Pentachlorobenzene 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.05 J 0.00 U 0.10

Endosulfan II 0.01 J 0.00 U 0.00 U 0.02 J 0.00 U 0.00 U 0.05 0.19

Endosulfan I 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.04 0.15

Endosulfan Sulfate 0.00 U 0.00 U 0.01 J 0.00 U 0.00 U 1.13 0.03 J 0.29

Mirex 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Chlorpyrifos 0.00 U 0.00 U 0.00 U 0.00 U 1.33 0.13 0.08 0.62

Total DDT 0.00 0.00 0.00 0.01 1.31 3.61 0.50 0.86

Notes: J, below method detection level, MDL; U, not detected
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65Appendices

Compound 1-1P 1-2P 1-3P 1-4P 1-5P 2-16P

Monobutyltin 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 5.57

Dibutyltin 0.00 U 1.54 0.00 U 0.26 J 1.67 5.37

Tributyltin 0.00 U 1.08 3.27 0.00 U 0.90 6.00

Tetrabutyltin 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Compound 2-19P 2-20P 2-24A 3-32P 3-33P 3-37A

Monobutyltin 1.14 20.88 0.99 0.61 0.00 U 0.00 U

Dibutyltin 0.56 21.20 1.30 0.58 0.00 U 0.00 U

Tributyltin 0.36 31.14 1.01 0.58 0.00 U 0.00 U

Tetrabutyltin 0.00 U 0.95 U 0.00 U 0.00 U 0.00 U 0.00 U

Compound 3-38A 3-45A 4-46P 4-47P 4-48P 4-49P

Monobutyltin 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Dibutyltin 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Tributyltin 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Tetrabutyltin 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Compound 4-50P 5-61P 5-62P 5-70A 5-71A 5-75A

Monobutyltin 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 2.37

Dibutyltin 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 2.28

Tributyltin 0.00 U 0.00 U 0.00 U 0.15 J 0.00 U 0.00 U

Tetrabutyltin 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U 0.00 U

Compound BB-1 BB-2 ML-2 ML-10

Monobutyltin 20.01 308.33 1.36 5.55

Dibutyltin 43.32 276.20 2.58 4.11

Tributyltin 76.59 247.83 1.91 2.0

Tetrabutyltin 0.35 J 1.86 0.00 U 0.00 U

Appendix G. Butyltins detected in sediments from the St. Thomas East End Reserves (ng Sn/dry g).
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Element Name 1-1P 1-2P 1-3P 1-4P 1-5P 2-16P 2-19P

Ag Silver 0 U 0 U 0 U 0 U 0 U 0 U 0 U

Al Aluminum 63,800 50,000 54,300 3,520 37,400 31,500 3,620

As Arsenic 12.4 9.12 7.18 1.82 6.66 8.14 1.89

Ca Calcium 77,600 115,000 98,700 365,000 201,000 20,700 363,000

Cd Cadmium 0.212 0 U 0.264 0 U 0 U 0.19 0 U

Cr Chromium 35.7 31.1 32.3 11 23.4 17.5 13.6

Cu Copper 69.9 60.5 69.3 5.55 36.9 46.8 14.7

Fe Iron 40,900 32,300 35,400 2,420 23,800 20,100 2,310

Hg Mercury 0.109 0.0676 0.0808 0.0028 0.0433 0.0658 0.0039

Mn Manganese 317 299 338 45.2 190 182 45.4

Ni Nickel 15.1 11.6 11.4 4.46 9.89 7.44 5.04

Pb Lead 21.1 31 25.3 1.26 14.9 12.9 2.34

Sb Antimony 0.487 0.632 0.819 0 U 0.426 0.482 0 U

Se Selenium 0.926 0.585 0.632 0.129 0.53 0.474 0.121

Si Silicon 181,000 B 147,000 174,000 18,400 106,000 B 126,000 27,700

Sn Tin 3.95 2.33 2.65 0 U 1.71 1.36 0 U

Zn Zinc 136 159 154 13.3 82.6 83.3 20.3

Element Name 2-20P 2-24A 3-32P 3-33P 3-37A 3-38A 3-45A

Ag Silver 0 U 0 U 0 U 0 U 0 U 0 U 0 U

Al Aluminum 22,600 1,380 8,860 1,210 979 9,430 2,360

As Arsenic 6.16 1.34 1.58 0 U 0 U 1.16 0 U

Ca Calcium 293,000 391,000 368,000 355,000 392,000 188,000 152,000

Cd Cadmium 0 U 0 U 0 U 0 U 0 U 0 U 0 U

Cr Chromium 17.1 4.91 11 9.5 8.26 12.7 9.17

Cu Copper 155 4.1 7.61 1.39 1.33 4.51 3.08

Fe Iron 14,600 1,200 5,010 761 582 4,910 1,230

Hg Mercury 0.0683 0.0021 0.0057 0.0012 0.0011 0.0009 0.0013

Mn Manganese 113 19.8 73.7 18.3 12.9 82.7 26.3

Ni Nickel 8.01 5.15 5.95 4.48 4.57 5.9 5.01

Pb Lead 19.2 0.782 2.55 0.785 0.615 1.12 0.824

Sb Antimony 0 U 0 U 0 U 0 U 0 U 0 U 0 U

Se Selenium 0.298 0.247 0.181 0.132 0.127 0.0913 0.163

Si Silicon 70,700 B 10,500 B 44,100 B 6,480 B 5,680 B 48,000 B 12,000 B

Sn Tin 2.52 0 U 0 U 0 U 0 U 0 U 0 U

Zn Zinc 115 9.42 15.8 0 U 5.04 12 5.22

Notes: U, analyte not detected; B, analyte detected in the procedural blank greater than 2X MDL. NA, not analyzed 

Appendix H. Major and trace elements detected in sediments from St. Th omas East End Reserves (μg/dry g).
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Element Name 4-46P 4-47P 4-48P 4-49P 4-50P 5-61P 5-62P

Ag Silver 0 U 0 U 0 U 0 U 0 U 0 U 0 U

Al Aluminum 3,250 5,130 4,840 2,840 2,430 2,680 3,550

As Arsenic 1.33 1.86 1.08 1.79 0 U 0 U 1.2

Ca Calcium 366,000 373,000 361,000 376,000 370,000 226,000 361,000

Cd Cadmium 0 U 0 U 0 U 0 U 0 U 0 U 0 U

Cr Chromium 11.7 11.7 20.8 5.75 6.43 6.46 12.2

Cu Copper 1.8 1.63 1.87 2.21 1.3 1.35 2.64

Fe Iron 1,850 2,980 3,110 1,940 996 1,090 2,110

Hg Mercury 0.0009 0.0011 0.0009 0.0007 0 U 0.0012 0.0016

Mn Manganese 37.4 54.7 47.1 47.1 19.8 19.3 43.7

Ni Nickel 5.05 5.11 7.93 4.64 4.29 4.9 4.97

Pb Lead 0.579 0.402 0.605 0.548 0.371 0.547 0.771

Sb Antimony 0 U 0 U 0 U 0 U 0 U 0 U 0 U

Se Selenium 0.152 0.0842 0.14 0.0698 0.0948 0.0946 0.14

Si Silicon 20,300 B 30,200 B 22,000 B 20,400 B 15,500 B 13,400 B 16,400 B

Sn Tin 0 U 0 U 0 U 0 U 0 U 0 U 0 U

Zn Zinc 6.5 11.5 9.46 12.2 9.39 3.88 5.86

Element Name 5-70A 5-71A 5-75A BB-1 BB-2 ML-2 ML-10

Ag Silver 0 U 0 U 0 U 0 U 0 U 0 U 0 U

Al Aluminum 4,060 3,170 3,390 41,700 52,700 53,200 45,100

As Arsenic 1.15 0 U 0 U 9.99 13.7 12 6.81

Ca Calcium 373,000 340,000 104,000 NA NA NA NA

Cd Cadmium 0 U 0 U 0 U 0.285 0 U 0.371 0.297

Cr Chromium 7.54 10.5 9.03 29.5 40.4 35.3 28.8

Cu Copper 3.4 2.48 4.74 145 1,010 78.9 60.6

Fe Iron 2,020 1,770 1,740 26,900 29,600 36,400 29,900

Hg Mercury 0.0018 0.0017 0.0011 0.11 0.34 0.123 0.0763

Mn Manganese 35.5 36.4 31.7 213 220 270 379

Ni Nickel 6.03 4.96 4.92 8.89 10.1 13.5 8.76

Pb Lead 0.815 0.875 0.69 24.8 81.2 27.9 20

Sb Antimony 0 U 0 U 0 U 0.393 0.687 0.743 0.669

Se Selenium 0.113 0.105 0.129 0.55 0.438 1.12 0.577

Si Silicon 17,200 B 14,600 B 12,600 B 130,000 169,000 120,000 191,000

Sn Tin 0 U 0 U 0 U 3.48 13.6 5.49 2.5

Zn Zinc 7.59 6.72 10.7 195 392 162 139

Notes: U, analyte not detected; B, analyte detected in the procedural blank greater than 2X MDL. NA, not analyzed

Appendix H. Major and trace elements detected in sediments from St. Thomas East End Reserves (μg/dry g). (continued)
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Appendix I. Trace elements plotted against aluminum and calcium.
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69Appendices

Appendix I. Trace elements plotted against aluminum and calcium (continued).
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Site Sample composition % water % sediment Cperf dry (CFU/g)

1-1P muddy shells 70.83 29.17 197

1-2P watery shells 66.67 33.33 3,493

1-3P muddy shells 62.12 37.88 2,137

1-4P sandy shells 45.16 54.84 33

1-5P muddy shells 64.71 35.29 714

2-16P watery shells 33.33 66.67 127

2-19P sandy shells 34.38 65.63 25

2-20P watery shells 51.43 48.57 159

2-24A shells 47.62 52.38 24

3-32P sandy 40.68 59.32 61

3-33P shells and sand 37.50 62.50 6

3-37A shells sandy 26.47 73.53 0

3-38A sandy 31.67 68.33 0

3-45A shells watery 37.88 62.12 0

4-46P sandy 26.39 73.61 0

4-47P sandy 23.29 76.71 0

4-48P shells and sand 23.53 76.47 0

4-49P shells sandy 30.95 69.05 0

4-50P sandy 28.57 71.43 0

5-61P sandy 28.33 71.67 5

5-62P sandy 28.77 71.23 0

5-70A rocky sandy 34.38 65.63 0

5-71A sandy 30.65 69.35 0

5-75A sandy 36.99 63.01 0

BB-1 watery mud 59.62 40.38 63

BB-2 rocky mud 37.74 62.26 31

ML-2 hairy mud 85.25 14.75 234

ML-10 black mud 56.86 43.14 2,558

Notes: CFU, colony forming units

Appendix J. Clostridium perfringens in sediments from the St. Thomas East End Reserves.

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