NOAA TECHNICAL MEMORANDUM NOS NCCOS 157

June 2013

NOAA NCCOS Center for Coastal Monitoring and Assessment

An Assessment of Chemical Contaminants Detected in Passive 

Water Samplers Deployed in 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.
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, Stanley Lateski, Nikita Thompson and Alexis Sabine of 

the University of the Virgin Islands (UVI), and Rob Ferguson and Marlon Hibbert of NOAA’s CRCP, and Jason Griffi th, 

for help with the planning, logistics, and fi eld work along with interpretation of results. Finally, we would like to acknowledge David Alvarez and Edward Furlong of the US Geological Survey for their analysis of the POCIS and help with 

interpretation of the results. 

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, F.R. Galdo, Jr., R.A. Warner, C.F.G. Jeffrey, A.M. Hoffman, D.A. Apeti, and S.J. 

Pittman. 2013. An assessment of chemical contaminants detected in passive water samplers deployed in the St. Thomas 

East End Reserves (STEER). NOAA Technical Memorandum NOS/NCCOS 157. Silver Spring, MD. 22 pp.
An Assessment of Chemical Contaminants Detected in Passive 

Water Samplers Deployed in the St. Thomas East 

End Reserves (STEER)

1

NOAA/NOS/National Centers for Coastal Ocean Science

Center for Coastal Monitoring and Assessment (CCMA)

Coastal Oceanographic Assessment, Status and Trends (COAST) Branch

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

Silver Spring, MD 20910

June 2013

2

The University of the Virgin Islands

St. Thomas, USVI

3

The Nature Conservancy

St. Thomas, USVI

Anthony S. Pait1, S. Ian Hartwell1, Andrew L. Mason1, Francis R. Galdo Jr.2, 

Robert A. Warner1, Christopher F. G. Jeffrey1, Anne M. Hoffman3, 

Dennis A. Apeti1

, and Simon J. Pittman1, 2

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

NOAA Technical Memorandum NOS NCCOS 157

STEER Stormwater Contaminants Report

Introduction

1

Abstract

This report is the second in a series from a project to assess land-based sources of pollution (LBSP) and effects 

in the St. Thomas East End Reserves (STEER) in St. 

Thomas, USVI, and is the result of a collaborative effort 

between NOAA’s National Centers for Coastal Ocean 

Science, the USVI 

Department of 

Planning and 

Natural Resources, 

the University of 

the Virgin Islands, 

and The Nature 

Conservancy. 

Passive water samplers (POCIS) were 

deployed in the 

STEER in February 2012. Developed by the US 

Geological Survey 

(USGS) as a tool to 

detect the presence 

of water soluble 

contaminants in 

the environment, 

POCIS samplers 

were deployed in the STEER at fi ve locations. In addition 

to the February 2012 deployment, the results from an earlier POCIS deployment in May 2010 in Turpentine Gut, a 

perennial freshwater stream which drains to the STEER, 

are also reported. 

A total of 26 stormwater contaminants were detected at 

least once during the February 2012 deployment in the 

STEER. Detections were high enough to estimate ambient water concentrations for nine contaminants using 

USGS sampling rate values. From the May 2010 deployment in Turpentine Gut, 31 stormwater contaminants 

were detected, and ambient water concentrations could be 

estimated for 17 compounds. 

Ambient water concentrations were estimated for a number of contaminants including the detergent/surfactant 

metabolite 4-tert-octylphenol, phthalate ester plasticizers DEHP and DEP, bromoform, personal care products 

including menthol, indole, n,n-diethyltoluamide (DEET), 

along with the animal/plant sterol cholesterol, and the 

plant sterol beta-sitosterol. Only DEHP appeared to have 

exceeded a water quality guideline for the protection of 

aquatic organisms. 

Introduction

Located on the southeastern end of the island of St. Thomas, US Virgin Islands, the St. Thomas East End Reserves 

or STEER is a collection of Marine Reserves and Wildlife 

Sanctuaries (MRWS) that include Inner Mangrove Lagoon, 

Cas Cay/Mangrove Lagoon, St James, and Compass Point 

Salt Pond MRWS 

(Figure 1). In 

recognition of the 

connectivity of 

the natural, cultural and economic 

resources of these 

four Reserves, 

along with the 

need to protect and 

properly manage the area, the 

USVI Department 

of Planning and 

Natural Resources 

(DPNR), along 

with the University of the Virgin 

Islands (UVI), The 

Nature Conservancy and a local 

community group 

began development of a comprehensive management plan 

in 2008 which was subsequently completed in 2011. The 

STEER represents one of the most recently protected areas 

designated by the Territorial Government of the USVI, and 

is part of a larger, territory-wide system of marine protected 

areas (STEER, 2011). 

STEER Environment

The STEER comprises an area of 9.6 km2

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

boundary of the STEER includes the Mangrove Lagoon/

Benner Bay MRWS (Figure 1); the St. James MRWS forms 

the eastern boundary which includes the marine habitat 

surrounding the island of Great St. James and the north 

shore of Little St. James Island; to the south the STEER is 

bounded by Cas and Patricia Cays and the southwest corner 

of Little St. James Island; the northern boundary is primarily the St. Thomas shoreline.

Within the STEER there are extensive mangroves and 

seagrass beds, along with coral reefs, lagoons and cays. 

The largest remaining mangrove system in St. Thomas 

occurs along the shores of Mangrove Lagoon/Benner Bay 

(IRF 1993). Mangroves offer many ecological benefi ts 

including natural buffers against shore erosion and shelter 

View into Cowpet Bay, within the St. Th omas East End Reserves (STEER). 

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STEER Stormwater Contaminants Report

Introduction

2

for juvenile fi sh and other organisms among the mangrove 

roots (DPNR-DFW, 2005). The extensive areas of seagrass in Benner and Jersey Bays provide habitat for many 

organisms including juvenile fi sh, and are an important 

food source for fi sh, turtles, birds and sea urchins. Conch 

feed off the epiphytes on the seagrass leaves (DPNR-DFW, 

2005). The STEER also contains signifi cant patch and 

fringing coral reef areas in Jersey Bay and in an area just 

south of Cas and Patricia Cays, along with St. James Bay. 

Species of coral found in the STEER include boulder star 

coral (Montastraea annularis), brain corals (Diploria spp)., 

various species of Porites, and staghorn coral (Acropora 

cervicornis) (DPNR-DFW, 2005). The STEER is thought to 

be one of the most valuable nursery areas remaining in St. 

Thomas, with numerous species of fi sh and shellfi sh spending some portion of their lives in the protected areas around 

the mangrove roots and in the seagrass beds (STEER, 

2011). 

The watersheds (Jersey Bay and Red Hook watersheds) 

around the STEER contain a variety of land uses. The 

Jersey Bay watershed drains to the STEER west of Deck 

Point. The watershed includes a large active landfi ll, numerous marinas and resorts, various commercial/industrial 

activities, an EPA Superfund Site, a horse racetrack, and 

residential areas served by individual septic systems, all of 

which have the potential to contribute point and nonpoint 

source pollution to the STEER. The Red Hook watershed 

(east of Deck Point) contains various commercial activities 

along with numerous marinas and resorts. 

The area that borders the western side of Mangrove Lagoon 

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

St. Thomas, but receives solid waste from St. John as well. 

The landfi ll covers approximately 330 acres, with 40 acres 

directly adjacent to Mangrove Lagoon (IRF, 1993). On the 

northern side of Mangrove Lagoon is the Clinton Phipps 

Racetrack. There are also numerous marinas in Benner Bay, 

serving both residents and transient boaters, along with 

signifi cant residential areas in the Jersey Bay watershed. 

Along the north shores of Jersey Bay, Cowpet Bay and 

Great Bay, are a series of resorts/hotels, condominiums (see 

inset, page 1) and yacht clubs. 

Elevated levels of chemical contaminants have been documented in the STEER watersheds (EPA, 2011). However, 

the extent of chemical contamination and biological effects 

or bioeffects in the STEER are currently unknown, but data 

on land-based sources of pollution (LBSP) and effects are 

needed in order to make better informed decisions regarding both land use and coastal resource management. 

NOAA/NCCOS Involvement in the STEER

At the NOAA Coral Reef Ecosystem Integrated Observing 

System (CREIOS) Meeting in 2009, representatives from 

DPNR identifi ed the STEER as a priority area and noted 

there were signifi cant data and information gaps in terms 

Figure 1. Individual Reserves that comprise the STEER. 
STEER Stormwater Contaminants Report

Introduction

3

of the types of chemical contaminants present, their concentrations, effects, and the overall health of the biological 

community within the STEER. 

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

Coastal Ocean Science (NCCOS), in partnership with 

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 and received funding from NOAA’s 

Coral Reef Conservation Program (CRCP), to develop an 

integrated assessment of chemical 

contamination and biological conditions within the STEER. This work 

is being done in coordination with 

development of a watershed management plan and a coastal use assessment. 

POCIS

Year 1 of the project included the 

quantifi cation of chemical contaminants in sediments, a bioeffects 

and benthic infaunal assessment, 

initiation of monthly sampling for 

nutrients and total suspended solids 

(TSS), and sedimentation using sediment traps at fi ve locations within the 

STEER (Pait et al., 2013). 

Work in Year 1 also included the 

deployment of passive water samplers, specifi cally Polar 

Organic Chemical Integrative Samplers or POCIS, developed by the US Geological Survey (USGS). In developing 

the POCIS, USGS worked to create a system to monitor 

water soluble contaminants and estimate their water concentrations. 

The goals of using the POCIS in the STEER were to assess 

the presence, and when possible estimate ambient concentrations of specifi c contaminants, and to evaluate seasonal 

differences. Although the concentration and effects of 

chemical contaminants in sediments in the STEER have 

been reported (Pait et al., 2013), there are many chemical 

contaminants that don’t readily accumulate in sediments, 

but are toxic to biota (e.g., some current use pesticides). 

Determining the presence and estimating the concentration 

of water soluble, specifi cally stormwater contaminants, 

provides additional information on stressors present in the 

STEER. The fi rst deployment of POCIS in the STEER 

was made in February 2012 during the dry season in St. 

Thomas; the second deployment was made in September 

2012 during the wet season. This report covers results from 

the fi rst deployment of the POCIS; the results from the second deployment will be covered in a later publication. 

The POCIS (Figure 2) is a disk consisting of a sorbent 

matrix sandwiched between two membrane sheets (Alvarez 

et al., 2008). The porous membrane sheets allow water to 

fl ow through the sorbent, enabling the sorbent material to 

sequester (accumulate) the contaminants of interest. The 

sorbent matrix can be tailored to the types of chemical contaminants of interest (e.g., stormwater chemicals or human 

use pharmaceuticals). For deployment, the POCIS disks are assembled 

onto a frame and then placed in the 

deployment canister (Figure 3). 

Many stormwater chemical contaminants, if present in the aquatic 

environment, are at very low concentrations, typically in the low parts per 

billion (ppb or ug/L) to parts per trillion (ppt or ng/L) ranges. A classic 

approach for detecting compounds 

at very low concentrations in the 

aquatic environment has been to collect, fi lter and extract large volumes 

of water, to enable their detection 

by analytical instrumentation. The 

POCIS disk, however, can potentially 

sample tens to hundreds of liters of 

water during deployment, providing time-weighted concentration estimates of contaminants 

present in the water column (Alvarez et al., 2008). This 

technology also has an advantage over discrete water 

samples, as POCIS can sequester chemical contaminants 

that may be present in the water only episodically, such 

as during storm events or during a small discharge or spill 

(Alvarez et al., 2008). Typical deployments of the POCIS 

last approximately 30 days. 

The USGS has also devised a method to estimate the 

ambient water concentration for a number of stormwater 

contaminants sequestered by the POCIS, using individual 

sampling rate values (Rs

). The Rs values are experimentally 

determined for each chemical, and incorporated into the 

following equation: 

 Cw = N 

 Rs

t

where 

Cw is the ambient water concentration of the chemical

N = the amount of chemical accumulated by the POCIS

Rs

 is the sampling rate (L/d), i.e., liters of water cleared of 

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Figure 2. Example of a POCIS disk. Im- P

age courtesy of the USGS.
Materials and Methods

4

STEER Stormwater Contaminants Report

analyte per day, and

t is the number of days of deployment for the POCIS. 

The number of days the POCIS 

is deployed is used in calculating estimated concentrations of 

the chemicals of interest, providing fl exibility in the length 

of time the POCIS is deployed. 

Additional information on the 

development and use of POCIS 

can be found in Alvarez et al. 

(2004, 2008). 

Materials and Methods

The POCIS deployment canisters containing the POCIS disks 

(two stormwater POCIS disks 

per canister) were shipped on 

ice to the University of the Virgin Islands in sealed solventrinsed metal cans. Upon arrival 

at UVI, the cans with the canisters were placed in a freezer 

until deployment. 

The POCIS deployment canisters were placed in the 

STEER on 16 February 2012 at fi ve locations (Figure 4), 

by scientists from UVI, and DPNR’s Division of Fish and 

Wildlife. The fi ve sites where the POCIS were deployed 

are the same targeted (not randomly selected) sites currently being used for the monthly sampling in the STEER 

(nutrients, TSS and sedimentation) by UVI, as part of the 

project. At each of 

these sites, sediment 

traps are attached to 

rods secured in the 

sediments. The POCIS 

deployment canisters 

were tethered to these 

same rods, by UVI and 

DPNR SCUBA divers. 

An example of one of 

the POCIS canisters 

deployed in the STEER 

can be seen in Figure 5.

A summary of conditions at each site at the 

time of POCIS canister 

deployment is provided 

in Table 1. The depth 

of the POCIS deployment canisters ranged from 1 meter at the site in Benner 

Bay, to 12.2 meters at the site adjacent to Great St. James 

Island. Each POCIS deployment canister was set between 

20 and 50 cm from the bottom. 

As part of some preliminary work in 2010, a POCIS deployment canister was placed in Turpentine Gut, the only 

perennial stream in St. Thomas (Nemeth and Platenberg, 

Figure 4. Locations of passive water samplers (POCIS) in the STEER.

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Figure 3. A disassembled POCIS deployment canister with 

the POCIS disks. Image courtesy of the USGS. 
Materials and Methods

5

STEER Stormwater Contaminants Report

2007). Although Turpentine Gut is not within the boundaries of the STEER, it drains directly to Mangrove Lagoon 

(Figure 4), and is not only a signifi cant source of freshwater 

to the STEER, but also of sediments (STEER, 2011), and 

other types of nonpoint source pollution including chemical 

contaminants. 

The POCIS deployment 

canister in Turpentine 

Gut was suspended in the 

water column at a depth of 

approximately 1.5 meters 

(Table 1). As with the 

2012 deployment, two POCIS stormwater disks were 

included in the deployment canister. NOAA and 

DPNR Division of Fish 

and Wildlife personnel 

placed the POCIS deployment canister approximately 20 meters south of the 

“Bridge to Nowhere” on 

the east bank of Turpentine 

Gut. 

Field blank canisters were 

used in both the 2012 and 

2010 deployments. The fi eld blank, a POCIS disk and 

frame, was exposed to the air during the time the POCIS 

canisters were being deployed, in order to assess the presence of airborne contamination. 

During the 2012 deployment in the STEER, the same fi eld 

blank was exposed to the air at each of the fi ve sites, and 

served as a cumulative fi eld blank. For the 2010 deployment in Turpentine Gut, one fi eld blank was used. After a 

POCIS deployment canister entered the water, the POCIS 

fi eld blank was placed back in its protective canister (solvent-rinsed metal container also used for shipping), sealed 

and then returned to UVI and placed in a freezer. 

The fi ve POCIS 

deployment canisters 

from the STEER 

were retrieved by 

UVI and DPNR 

Division of Fish and 

Wildlife scientists 

using SCUBA on 14 

March 2012. During 

the time the POCIS 

deployment canisters were out of the 

water, the fi eld blank 

was again opened 

and exposed to the 

air. Once retrieved, 

the POCIS deployment canisters were 

returned to their 

protective canisters, 

and then placed in 

the freezer at UVI 

until they were shipped on ice along with the fi eld blank to 

the USGS for analysis. Additional information on POCIS 

deployment techniques can be found in Alvarez (2010). 

At the USGS laboratory, the POCIS disks were removed 

from the deployment canisters, and dichloromethane and 

methyl-tert-butyl ether were used to extract the stormwater contaminants accumulated by the POCIS, for analysis. 

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traps at a site in the STEER. 

Table 1. Location and conditions during deployment of the POCIS canisters in February 2012 and May 2010. 

Site Date Latitude Longitude Deployment 

Depth (m) Water Conditions

Great St. James (SJ) 2/16/2012 18.30302 -64.83671 12.2 Clear, calm

Cowpet Bay (CB) 2/16/2012 18.31487 -64.84267 5.5 Clear, calm

Rotto Cay (RC) 2/16/2012 18.31331 -64.86423 5.5 Clear, calm

Benner Bay (BB) 2/16/2012 18.3167 -64.8674 1 High turbidity

Mangrove Lagoon (ML) 2/16/2012 18.31385 -64.87988 1.3 High turbidity

Turpentine Gut (2010) (TG) 5/5/2010 18.32046 -64.87719 1.5 Moderate flow, high turbidity

Note - depth of POCIS canister in meters (m)
Materials and Methods 6

STEER Stormwater Contaminants Report Table 2. Stormwater contaminants analyzed from the POCIS deployed in the St. Thomas East End Reserves (STEER) in 2012, and from Turpentine Gut (2010). Compound Use/Source Compound Use/Source 1,4-Dichlorobenzene Moth repellant, fumigant, deodorizer Ethyl citrate Plasticizer 1-Methylnapthalene Alkylated PAH (polycyclic aromatic hydrocarbon) Fluoranthene Polycyclic aromatic hydrocarbon (PAH) 2,6-Dimethylnapthalene Alkylated PAH (polycyclic aromatic hydrocarbon) Galaxolide (HHCB) Synthetic fragrance 2-Methylnapthalene Alkylated PAH (polycyclic aromatic hydrocarbon) Indole Component of fragrances 3,4-Dichlorophenyl isocyanate Degradation product of the herbicide diuron or linuron Isoborneol Natural insect repellent 3-Beta-coprostanol Fecal indicator Isophorone Solvent 4-Cumylphenol Detergent metabolite Isoquinoline Flavor and fragrance ingredient 4-n-Octylphenol Detergent metabolite Menthol Decongestant 4-Tert-octylphenol Detergent metabolite Metalaxyl Fungicide 5-Methyl-1H-benzotriazole Anticorrosive used in antifreeze Methyl salicylate Liniment, flavoring agent

Acetophenone Fragrance used in detergent and tobacco Metolachlor HerbicideAnthracene Polycyclic aromatic hydrocarbon (PAH) N,N-diethyltoluamide (DEET) Mosquito repellentAnthraquinone Used in the manufacture of dyes/textiles and seed treatment Naphthalene Polycyclic aromatic hydrocarbon (PAH), also a fumigantAtrazine Herbicide NPEO1 Detergent metaboliteBenzo(a)pyrene Polycyclic aromatic hydrocarbon (PAH) NPEO2 Detergent metaboliteBenzophenone Component of perfumes and soaps OPEO1 Detergent metaboliteBeta-sitosterol Plant sterol OPEO2 Detergent metaboliteBHA Food additive, preservative Para-cresol Wood preservativeBisphenol A Manufacturing resin Para-nonylphenol Detergent metaboliteBromacil Herbicide PBDE-47 Flame retardantBromoform Byproduct of water chlorination Pentachlorophenol Wood preservativeCaffeine Stimulant Phenanthrene Polycyclic aromatic hydrocarbon (PAH)Camphor Fragrance in personal-care products Phenol Disinfectant, manufacturing intermediateCarbaryl Insecticide Prometon HerbicideCarbazole Used in the manufacture of dyes and lubricants Pyrene Polycyclic aromatic hydrocarbon (PAH)Chlorpyrifos Insecticide Skatol Present in feces and coal tarCholesterol Plant/animal sterol Stigmastanol Plant sterolCotinine Nicotine metabolite Tetrachloroethylene Dry cleaningCumene Paint thinner, used in the production of phenol and acetone Tonalide (AHTN) Synthetic fragranceDiazinon Insecticide Tri(2-chloroethyl)phosphate Plasticizer, flame retardantDichlorvos Insecticide (e.g., used in pet collars) Tri(dichlorisopropyl)phosphate Flame retardantDiethyl phthalate Plasticizer Tributylphosphate Anti-foaming agent, fire retardantDiethylhexyl phthalate Plasticizer Triclosan Disinfectant, antimicrobiald-Limonene Antimicrobial, fungicide, fragrance Triphenyl phosphate Plasticizer, flame retardantEthanol,2-butoxy-,phosphate Flame retardantAbbreviations: BHA, Butylated hydroxyanisole, PBDE-47 polybrominated diphenyl ether congener 47; NPEO1, nonlyphenol monoethoxyalte; OPEO2, octylphenol diethoxylate
p. 7 7 Results and Discussion

STEER Stormwater Contaminants Report

The analysis of the extracts from the POCIS was carried 

out using gas chromatography/mass spectrometry in the 

selected ion monitoring mode, and results were reported 

in a quantity of each chemical per POCIS extract (i.e., ng/

ampoule). The sampling rate values (Rs

) mentioned earlier 

were then used to estimate ambient water concentrations of 

those compounds found to be above the Quantitation Level. 

The Quantitation Level is the minimum concentration of 

the stormwater contaminant in the POCIS extract needed to 

ensure confi dence in the reported values, and ultimately in 

the estimated ambient water concentration. Additional information on the analysis of the POCIS disks can be found 

in Alvarez et al. (2008). 

The 69 stormwater contaminants analyzed from the POCIS 

are listed in Table 2, and include a number of pesticides, 

detergent metabolites, animal and plant sterols, fl ame 

retardants, fecal indicators and ingredients in personal care 

products. 

Pesticides include the herbicides atrazine, metolachlor and bromacil, and the 

insecticides chlorpyrifos, 

carbaryl, and diazinon. The 

metabolites of the surfactants/

detergents included 4-octylphenol and para-nonylphenol, 

along with nonyl- and octylphenol polyethoxylates 

such as NPEO1 (nonylphenol 

monoethoxylate) and OPEO2 

(octylphenol diethoxylate). 

The environmentally ubiquitous phthalate ester plasticizers diethyl phthalate (DEP) 

and diethylhexyl phthalate or DEHP, are also sequestered 

by POCIS. DEHP has been linked to endocrine disruption. 

A number of animal and plant-related compounds accumulated by the POCIS include the animal/plant sterol cholesterol, and the plant sterols beta-sitosterol and stigmastanol. 

Fecal indicators 3-beta-coprostanol and skatol are also 

sequestered by POCIS. 

Results and Discussion

The raw data from the POCIS deployed in February 2012 

at the fi ve sites in the STEER can be found in Appendix A; 

the raw data from the May 2010 deployment in Turpentine 

Gut can be found in Appendix B. These appendices provide the concentration of each contaminant which resulted 

from extracting the two POCIS disks in each deployment 

canister. The units, ng/ampoule, represents the concentration of each analyte in the ampoule of the fi nal extract from 

the POCIS disks.

A total of 26 stormwater contaminants were detected 

at least once in the STEER (Appendix A), although the 

majority (65%) of detections for these 26 were below the 

Quantitation Level. In Turpentine Gut, 31 stormwater contaminants were detected, a little over half (55%) of these 31 

were below the Quantitation Level. Concentrations above 

the Quantitation Level are used to estimate ambient water 

concentrations. 

Table 3 presents the estimated ambient water concentrations of the stormwater contaminants accumulated by the 

POCIS disks in the STEER and also in Turpentine Gut. 

The shading in Table 3 indicates those stormwater contaminants in the POCIS that were high enough to estimate 

ambient water concentrations. 

The Reporting Limit in Table 

3 represents the lower limit for 

estimating the ambient water 

concentration of a stormwater 

contaminant, and is calculated 

from the Quantitation Level (see 

Appendix A).

There are fewer stormwater 

contaminants listed in Table 3 

than in Appendix A and B. A 

number of compounds, including 

the polycyclic aromatic hydrocarbons (PAHs) such as 1-methylnapthalene, anthracene and 

benzo(a)pyrene, along with the 

polybrominated fl ame retardant 

PBDE-47 and the wood preservative pentachlorophenol are 

not included in Table 3. The POCIS disks are not effi cient 

samplers of these compounds and as a result are only occasionally detected in the POCIS (Alvarez, pers. comm.). 

Estimated Concentrations of Stormwater Contaminants in 

the STEER (2012) 

There appear to be few published studies quantifying 

concentrations of the types of compounds analyzed for this 

project, particularly in the US Caribbean. The concentrations of stormwater contaminants estimated from this study 

are compared with recent results from St. John USVI, 

South Florida, California and also from the northwest 

Mediterranean Sea. 

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

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p. 8 8 Results and Discussion

STEER Stormwater Contaminants Report

Table 3. Estimated water column concentrations of stormwater contaminant residues sampled by POCIS in the STEER. 

Mangrove Lagoon Benner Bay Rotto Cay Cowpet Bay Great St. James Reporting Limit Turpentine Gut Reporting Limit

Compound ng/L ng/L ng/L ng/L ng/L ng/L ng/L ng/L

1,4-Dichlorobenzene <RL <RL <RL <RL <RL 130 <RL 100

3,4-Dichlorophenyl isocyanate (m) <RL <RL <RL <RL <RL 240 <RL 190

3-Beta-coprostanol (m) <RL <RL <RL <RL <RL 240 <RL 190

4-Cumylphenol (m) <RL <RL <RL <RL <RL 12 <RL 10

4-n-Octylphenol (m) <RL <RL <RL <RL <RL 5.2 <RL 4.2

4-Tert-octylphenol <RL <RL <RL <RL <RL 5.2 17 4.2

5-Methyl-1H-benzotriazole <RL <RL <RL <RL <RL 110 140 86

Acetophenone <RL <RL <RL <RL <RL 29 41 24

Anthraquinone (m) <RL <RL <RL <RL <RL 18 <RL 15

Atrazine <RL <RL <RL <RL <RL 20 <RL 16

Benzophenone <RL <RL <RL <RL <RL 36 <RL 30

Beta-sitosterol (m) <RL <RL 620 <RL <RL 480 <RL 380

BHA (m) <RL <RL <RL <RL <RL 73 <RL 61

Bisphenol A (m) <RL <RL <RL <RL <RL 1.9 6.2 1.5

Bromacil <RL <RL <RL <RL <RL 72 <RL 60

Bromoform 230 84 230 160 160 49 <RL 41

Caffeine <RL <RL <RL <RL <RL 19 <RL 16

Camphor <RL <RL <RL <RL <RL 35 45 29

Carbaryl (m) <RL <RL <RL <RL <RL 35 <RL 29

Carbazole <RL <RL <RL <RL <RL 8.1 <RL 6.7

Chlorpyrifos <RL <RL <RL <RL <RL 180 <RL 150

Cholesterol (m) <RL 1100 550 800 380 240 610 190

Cotinine (m) <RL <RL <RL <RL <RL 70 <RL 58

Cumene <RL <RL <RL <RL <RL 16 <RL 13

Diazinon <RL <RL <RL <RL <RL 22 <RL 18

Dichlorvos <RL <RL <RL <RL <RL 110 <RL 94

Diethyl phthalate 97 92 72 100 120 20 120 16

Diethylhexyl phthalate 77 66 65 83 300 29 1100 24

d-Limonene <RL <RL <RL <RL <RL 70 <RL 58

Ethanol,2-butoxy-,phosphate <RL <RL <RL <RL <RL 170 220 140

Ethyl citrate <RL <RL <RL <RL <RL 4.5 <RL 3.7

Galaxolide (HHCB) <RL <RL <RL <RL <RL 5.4 18 4.4

Indole <RL 17 <RL <RL <RL 14 110 11

Isoborneol <RL <RL <RL <RL <RL 35 <RL 29

Isophorone <RL <RL <RL <RL <RL 4.5 <RL 3.6

Isoquinoline <RL <RL <RL <RL <RL 14 <RL 12

Menthol <RL 200 <RL <RL <RL 150 <RL 120

Metalaxyl <RL <RL <RL <RL <RL 90 <RL 74

Methyl salicylate <RL <RL <RL <RL <RL 30 <RL 25

Metolachlor <RL <RL <RL <RL <RL 2.7 <RL 2.2

n,n-Diethyltoluamide (DEET) 7.6 <RL <RL <RL <RL 4.9 95 4.0

NPEO1-total (m) <RL <RL <RL <RL <RL 100 <RL 83

NPEO2-total (m) <RL <RL <RL <RL <RL 170 <RL 140

OPEO1 (m) <RL <RL <RL <RL <RL 17 <RL 13

OPEO2 (m) <RL <RL <RL <RL <RL 17 21 14

Para-cresol <RL <RL <RL <RL <RL 27 520 23

Para-nonylphenol-total (m) <RL <RL <RL <RL <RL 76 <RL 63

Phenol 150 250 <RL 29 <RL 25 35 20

Prometon <RL <RL <RL <RL <RL 10 <RL 9

Skatol <RL <RL <RL <RL <RL 21 20 17

Stigmastanol (m) <RL <RL <RL <RL <RL 240 <RL 190

Tetrachloroethylene (m) <RL <RL <RL <RL <RL 54 <RL 45

Tonalide (AHTN) <RL <RL <RL <RL <RL 5.2 <RL 4.3

Tri(2-chloroethyl)phosphate <RL <RL <RL <RL <RL 15 <RL 13

Tri(dichlorisopropyl)phosphate <RL <RL <RL <RL <RL 190 <RL 150

Tributylphosphate <RL <RL <RL <RL <RL 7.9 7.3 6.5

Triclosan <RL <RL <RL <RL <RL 4.9 <RL 4.0

Triphenyl phosphate <RL <RL <RL <RL <RL 47 <RL 39

Contaminant residues sampled by POCIS in the STEER; concentrations above the Reporting Limit for a compound are indicated by shading. POCIS, polar organic chemical 

integrative sampler; ng/L, estimated water concentration reported; (m), indicates a highly variable compound; <RL, less than the reporting limit. 

February 2012 POCIS Deployment May 2010 POCIS Deployment
p. 9 9 Results and Discussion

STEER Stormwater Contaminants Report

From the February 2012 deployment in the STEER, ambient water concentrations could be estimated for nine stormwater contaminants (Table 3). The highest estimated concentration for any of the compounds detected in the STEER 

was the animal/plant sterol cholesterol at the Benner Bay 

site (1,100 ng/L), followed by Cowpet Bay (800 ng/L) and 

Rotto Cay (550 ng/L). Somewhat surprisingly, cholesterol 

was not detected in the POCIS deployed in Mangrove Lagoon which receives direct input from Turpentine Gut. 

Bargar et al. (2013) conducted a study on nearby St. John, 

in the Virgin Islands National Park and the Virgin Islands 

Coral Reef National Monument. Cholesterol concentrations detected by Bargar et al. (2013) ranged from 240 

ng/L at Round Bay, to 

440 ng/L at Whistling 

Cay in the POCIS 

deployed, similar to the 

concentrations found 

in the STEER. Along 

the South Florida coast 

(Miami to Looe Key), 

concentrations ranged 

from below the detection limit to 2,896 ng/L 

(Singh et al. (2010). 

Cholesterol is an essential and natural 

component of cell 

membranes in animals, 

and is an ingredient 

in some personal care 

products. Cholesterol 

is found to a lesser degree in some plant and fungal species, 

and has sometimes been used as a fecal indicator (Francy et 

al., 2003). 

Another class of stormwater contaminant detected in the 

STEER by POCIS were two phthalate esters, diethylhexyl 

phthalate (DEHP), and diethyl phthalate (DEP). Phthalate esters are used to increase the fl exibility of plastics, 

particularly polyvinyl chloride (PVC), and have been used 

in a variety of products worldwide including table cloths, 

furniture, toys, medical tubing, personal care products, and 

food packaging. The highest estimated concentration of 

DEHP detected in the STEER was 300 ng/L at Great St. 

James. Due to health concerns regarding DEHP, including 

evidence that DEHP may be an endocrine disruptor (Gray 

et al., 2000) and a possible carcinogen (USDHHS, 2011), 

the use of DEHP has been reduced or eliminated for some 

applications. 

The highest estimated concentration of DEHP detected in 

St. John, USVI by Bargar et al. (2013) was 820 ng/L at 

Whistling Cay, somewhat higher than what was estimated 

in the current study at Great St. James. As noted earlier, 

the deployment of the POCIS in the STEER was made 

in February 2012, during the dry season. Lower rainfall 

levels would likely lead to less runoff, which in turn could 

result in lower concentrations of contaminants in the water 

column. The deployment of POCIS in St. John occurred in 

May, which Bargar et al. (2013) identifi ed as the beginning 

of the rainy season.

Alvarez et al. (in 

press) quantifi ed 

contaminants of 

emerging concern 

at 11 sites along the 

California coast including the Southern 

California Bight and 

San Francisco Bay. 

The mean estimated 

concentration of 

DEHP using POCIS 

was 400 ng/L, somewhat higher than the 

results in the STEER, 

and ranged from not 

detected to 1,100 

ng/L. In a study 

to assess organic 

micropollutants in coastal waters from the northwestern 

Mediterranean Sea (Catalonia to Valenica, Spain), SánchezAvila et al. (2012) sampled coastal seawater from 22 sites. 

DEHP was detected in over 90 percent of the water samples 

collected. The mean concentration was 145 ng/L, the maximum detected in coastal seawaters was 617 ng/L (SánchezAvila et al., 2012). 

The highest estimated ambient water concentration of DEP 

from the STEER was 120 ng/L, at the Great St. James 

site. The mean concentration of DEP estimated by Alvarez et al. (in press) in California from the POCIS was 150 

ng/L, similar to the highest estimated concentration in the 

STEER; the highest concentration estimated by Alvarez et 

al. (in press) was 600 ng/L. In the northwestern Mediterranean, the mean concentration of DEP detected in coastal 

seawaters was 253 ng/L with a maximum of 483 ng/L. 

DEP has also been identifi ed as a possible endocrine disA

p

co

em

at

C

cl

C

S

T

co

D

w

w

re

an

d

View into the St. Th omas East End Reserves (STEER). 
p. 10 10Results and Discussion

STEER Stormwater Contaminants Report

ruptor (Cólon et al., 2000). As noted earlier, the phthalate 

esters are ubiquitous environmental contaminants, and low 

levels of phthalates also appeared in the POCIS fabrication 

and fi eld blanks (Appendix A). 

 

Phenol had an estimated ambient water concentration of 

250 ng/L at the Benner Bay site, and 150 ng/L in Mangrove 

Lagoon. Phenol is a common intermediate used in the production of many types of compounds including detergents 

(e.g., alkylphenols) and plastics. Phenol is also used in oral 

antiseptics and as a disinfectant. Phenols can be released 

into the environment through wastewater treatment systems from either the direct use of phenol or degradation of 

phenolic compounds, and also as leachate from landfi lls, as 

materials containing phenols degrade (Masoner and Mashburn, 2004). As with the phthalate esters, phenol was a low 

level contaminant in the POCIS fabrication and fi eld blanks 

(Appendix A). Phenol was not detected in the POCIS deployed by Bargar et al. (2013) in St. John. 

In the marine environment, the presence of bromoform is 

often the result of algal metabolism (Palmer and Reason, 

2009). In freshwater, bromoform can be an indicator of the 

effects of chlorination or ozonation of drinking water, or 

from the chlorination of treated wastewater. The highest estimated bromoform concentration from the POCIS 

deployed in the STEER was 230 ng/L in Mangrove Lagoon and Rotto Cay, followed by 160 ng/L in Cowpet Bay 

and Great St. James Bay. In St. John, Bargar et al. (2013) 

detected concentrations of bromoform ranging from 73 

ng/L to 170 ng/L, similar to what was found in the STEER. 

In their work along the California coast, Alvarez et al. (in 

press), detected concentrations of bromoform ranging from 

5 ng/L to 77 ng/L; bromoform was detected in all POCIS 

samples. 

A number of fragrance-related compounds were detected in 

the POCIS in the STEER as well. Indole is used as a fragrance in personal care and household products (Lawrence 

and LaFontaine, 2010). The concentration of indole at the 

Benner Bay site was estimated at 17 ng/L, just above the 

Reporting Limit of 14 ng/L (Table 3). Indole was detected 

at two of the four sites in St. John, by Bargar et al. (2013) 

and the highest estimated concentration was 17 ng/L, the 

same as the Benner Bay site in the STEER. 

A number of other fragrances, including acetophenone, 

benzophenone, d-limonene, and galaxolide (HHCB) were 

detected at most of the STEER sites (Appendix A), but the 

concentrations were below the Reporting Limit (Table 3). 

Acetophenone and galaxolide were also below the Reporting Limit at the sites sampled by POCIS in St. John (Bargar 

et al., 2013). 

Estimates of the concentration of two other personal care 

product ingredients, including menthol and n,n-diethyltoluamide (DEET) could be made for the STEER. Menthol is 

used as a decongestant and analgesic and is an ingredient in 

some cigarettes. There was only one detection of menthol, 

at an estimated ambient water concentration of 200 ng/L 

from the POCIS placed in Benner Bay. The menthol could 

be related to cigarettes, however cotinine, a degradation 

product of nicotine, was not found in any of the POCIS 

deployed in the STEER or in Turpentine Gut. 

The highest estimated concentration of DEET in the 

STEER was 7.6 ng/L from the POCIS deployed in Mangrove Lagoon. DEET is an insect repellent and its use 

would not be surprising given the likely need for protection 

against mosquitos and other insect pests in the area. In St. 

John, DEET was detected but it was below the method detection limit (Bargar et al., 2013). On the California coast, 

DEET was detected in 60 percent of the POCIS deployed, 

with an average concentration of 10 ng/L, with a maximum 

concentration of 69 ng/L, lower than in the STEER (Alvarez et al., in press). Along the South Florida coast, DEET 

ranged from not detected to 68 ng/L (Singh et al., 2010). 

Finally, an estimated water concentration could be made 

for beta-sitosterol. The presence of this plant sterol typically results from the decay of plant materials from natural 

sources, and from the use and decay of paper products. The 

only occurrence for which an ambient water concentration 

of beta-sitosterol could be made in the STEER was at Rotto 

Cay with an estimated concentration of 620 ng/L, although 

beta-sitosterol was detected (but below the Reporting 

Limit) at all the other sites. 

A comparison of the number of compounds with estimated 

water concentrations in the STEER can be seen in Figure 5. 

Turpentine Gut had a greater number of compounds detected than the sites in the STEER. Where the same compound 

was detected in Turpentine Gut and in the STEER, the 

estimated concentration was typically higher in Turpentine 

Gut, but not always.

Although Mangrove Lagoon receives inputs from the Bovoni Landfi ll through runoff and inputs from surrounding 

residential/commercial areas and from Turpentine Gut, this 

did not seem to result in a greater number of stormwater 

contaminants in Mangrove Lagoon compared to the other 

POCIS sites in the STEER, as was expected. The sites in 

the STEER in Figure 5 are ordered in a west to east fash-
p. 11 11Results and Discussion

STEER Stormwater Contaminants Report

ion. There did not appear to be 

an obvious pattern or gradient 

in the number of compounds in 

the STEER, moving west to east 

away from Turpentine Gut and 

Mangrove Lagoon. There were 

four compounds with estimated 

ambient water concentrations 

in Mangrove Lagoon, however, 

there were fi ve compounds each 

at Benner Bay, Rotto Cay and 

Cowpet Bay. This also held true 

for the total number of compounds detected in the POCIS 

(Appendix A). Additional 

POCIS, perhaps offshore of these 

areas would provide more information, including the possibility 

of gradients. 

Estimated Concentrations of 

Stormwater Contaminants in 

Turpentine Gut (2010)

The deployment of the POCIS in Turpentine Gut was 

almost two years earlier than the POCIS deployed in the 

STEER. In addition, the deployment in Turpentine Gut and 

the STEER were done at somewhat different times of the 

year; mid-spring for Turpentine Gut, and mid to late winter 

for the POCIS deployment in the STEER. Nevertheless, 

the earlier POCIS deployment in Turpentine Gut provides a 

useful characterization of stormwater contaminants present 

in St. Thomas’ only perennial stream, and offers the opportunity to make some comparisons to what was found in the 

STEER.

As noted, ambient water concentrations could be estimated 

for a greater number of compounds in Turpentine Gut 

than in the STEER (Figure 5). Disregarding the temporal 

aspects of the deployment, these fi ndings are not surprising, 

as Turpentine Gut runs through the heart of the Jersey Bay 

watershed before it empties into Mangrove Lagoon, and 

likely receives input from a variety of sources. Land use in 

the Jersey Bay is roughly 30% low- and mid-density urban 

development, with the remaining land use primarily forest 

and shrub (62%) (Cadmus, 2011).

Two compounds, the plasticizer DEHP (1,100 ng/L) and 

the insect repellent DEET (95 ng/L), had higher estimated 

ambient water concentrations in Turpentine Gut than in the 

STEER sites. Both DEHP and DEET are common stormwater/wastewater contaminants, and their appearance in 

Turpentine Gut is not surprising. The higher DEHP concentration in Turpentine Gut was similar to the maximum 

concentration found by Bargar et al. (2013) in St. John (820 

ng/L), and was the same as the maximum found by Alvarez 

et al. (in press), along the California coast (1,100 ng/L). 

The estimated concentration of DEET found in Turpentine 

Gut was higher than the highest concentrations estimated 

by Alvarez et al. (in press) (69 ng/L) along the California 

coast, and by Singh et al (2010) (68 ng/L) in South Florida. 

There were 10 compounds in the POCIS for which ambient 

water concentration estimates could be made from Turpentine Gut, that were either not found or were below Reporting Limits at the sites in the STEER. Two of these were the 

detergent metabolites 4-tert-octylphenol and OPEO2. The 

estimated concentration of 4-tert-octylphenol in Turpentine 

Gut was 17 ng/L (Table 3). Bargar et al. (2013) did not detect 4-tert-octylphenol in the POCIS deployed in St. John. 

Bisphenol-A is also a plasticizer, used in the production of 

polycarbonate plastic, and in epoxy resins commonly applied to the insides of food and beverage cans. The estimated ambient water concentration in Turpentine Gut was 

6.2 ng/L. Bisphenol-A was detected by Singh et al. (2010) 

at concentrations up to 190 ng/L in South Florida. In coastal seawater, Sánchez-Avila et al. (2012) detected an average 

bisphenol-A concentration of 18 ng/L, ranging from 2.3 

ng/L to 102 ng/L. Bisphenol-A has also been identifi ed as 

an endocrine disruptor (Lindholst et al., 2000). 

There were three personal care product ingredients detected 

above the Reporting Limit in Turpentine Gut. Camphor (45 

Figure 5. Number of stormwater contaminants with estimated water column 

concentrations in the STEER and in Turpentine Gut.
p. 12 12Results and Discussion

STEER Stormwater Contaminants Report

ng/L) and galaxolide (18 ng/L) are fragrance ingredients. 

Acetophenone, used as a fragrance in laundry detergent and 

in cigarettes, was also identifi ed in Turpentine Gut at an 

estimated ambient concentration of 41 ng/L. As noted earlier, acetophenone was detected in the STEER at all sites, 

but below the Reporting Limit. Along the California coast, 

galaxolide was present in 80 percent of the POCIS samples, 

with a mean concentration of 150 ng/L, and acetophenone 

was also present in 80 percent of the samples from POCIS, 

with a mean concentration of 11 ng/L (Alvarez et al., in 

press). 

In Turpentine Gut, 5-methyl-1H-benzotriazole was detected 

at an estimated concentration of 140 ng/L. This compound 

is used as a corrosion inhibitor especially for copper and 

its alloys (e.g., brass), and is commonly found in antifreeze 

formulations for automobiles. 

Two fl ame retardants, ethanol,2-butoxy-,phosphate (220 

ng/L), and tributylphosphate (7.3 ng/L) were only found in 

the Turpentine Gut POCIS. Ethanol,2-butoxy-,phosphate 

is also used as a plasticizer and an antifoaming agent. In 

addition to being a fl ame retardant, tributylphosphate has a 

number of other uses including as a defoamer in detergent 

solutions and in paints and adhesives. Alvarez et al. (in 

press), estimated a mean tributylphosphate concentration of 

6.6 ng/L along the California coast, similar to the concentration estimated in Turpentine Gut. 

Para-cresol, used as a wood preservative, was detected 

in Turpentine Gut with an estimated water concentration 

of 520 ng/L. As with a number of the other stormwater 

contaminants, para-cresol was detected in the POCIS from 

all sites in the STEER, but was below the Reporting Limit 

(Appendix A). 

The fecal marker 3-methyl-1(H)-indole, or skatol, was 

detected at an estimated ambient water concentration in 

Turpentine Gut of 20 ng/L, just above the Reporting Limit 

of 17 ng/L. A second fecal indicator, 3-beta-coprostanol 

was also detected in Turpentine Gut (Appendix B), however, at a level too low to estimate a water concentration. 

The presence of both these fecal indicators from Turpentine 

Gut would seem indicative of inputs from septic systems 

and from animal (e.g., dog) waste. 

As noted earlier, no cotinine or caffeine was detected in the 

POCIS deployed in Turpentine Gut or in the STEER, which 

was somewhat surprising given the density of the population in this part of St. Thomas, and likely use of these 

compounds in tobacco products or in caffeinated beverages. Neither of these compounds were detected in POCIS 

deployed in St. John (Bargar et al., 2013). 

Comparison with Water Quality Criteria

Table 4 compares the concentrations of stormwater contaminants quantifi ed in the STEER and Turpentine Gut with 

available water quality criteria developed by the US Environmental Protection Agency (EPA) and others. It should 

be noted that the estimated water column concentrations 

represent ambient concentration, and as such would not 

refl ect peak concentrations as might occur after a rainstorm. 

The values in Table 4 for the STEER and Turpentine Gut 

have been converted to ug/L or ppb, in order to make the 

table more readable. It can be seen that almost all the 

estimated water concentrations of the contaminants listed 

in Table 4 from both the STEER and Turpentine Gut were 

below, in most cases orders of magnitude below, the criteria 

listed. The only exception was the plasticizer DEHP from 

Turpentine Gut. The estimated water concentration in 

Turpentine Gut (1.1 ug/L or 1,100 ng/L) is above a lower 

Table 4. Comparison of estimated concentrations of stormwater contaminants with available water quality criteria. 

Mangrove Benner Rotto Cowpet St. Turpentine

Acute Chronic Acute Chronic Lagoon Bay Cay Bay James Gut

Bromoform − − 2,300 320 0.023 0.084 0.23 0.16 0.16 −

Diethyl phthalate 2,944 3.4 1,800 110 0.097 0.092 0.072 0.1 0.12 0.12

Diethylhexyl phthalate 400 360 400 0.3-16 0.077 0.066 0.065 0.083 0.3 1.1

Para-cresol − − <230 <13 − −−− − 0.52

Phenol 5,800 400 10,200 180-320 0.15 0.25 − 0.029 − 0.035

Tetrachloroethylene 10,200 450 830 45 − −−− − −

Note: Marine/freshwater criteria and STEER concentrations are in ug/L or parts per billion, to make table more readable. Marine 

and freshwater criteria represent water guidelines developed by the USEPA and othes. Water Quality Criteria values taken

from NOAA Screening Quick Reference Tables (SQuiRTs, Buchman, 2008). 

Wastewater 

Contaminant

Estimated Concentrations (ug/L) - STEER and Turpentine Gut 

Marine (ug/L) Freshwater (ug/L)

Water Quality Criteria
Summary and Conclusions

13

STEER Stormwater Contaminants Report

chronic (longer-term exposure) criteria (0.3 ug/L) listed in 

Table 4. 

Finally, the compound tetrachloroethylene was included in 

Table 4. Within the watershed that drains to Turpentine Gut 

and the STEER, is the Tutu Wellfi eld Superfund Site. The 

EPA Superfund site was established due to contamination 

of groundwater and wells in the area by chlorinated volatile 

organic compounds (CVOC), including tetrachloroethylene. 

This compound was used extensively for dry cleaning by 

a textile plant located in the watershed that operated from 

1969 to 1982 (EPA, 2011). Contamination of the groundwater along with commercial and private wells in the Tutu 

area resulted in EPA establishing the Superfund site and installing groundwater treatment systems to remove CVOCs, 

including tetrachloroethylene (EPA, 2011).

From Table 4, it can be seen that there were no estimated 

water concentrations for tetrachloroethylene in either 

Turpentine Gut or in Mangrove Lagoon. There was one detection of tetrachloroethylene from the POCIS deployed adjacent to Great St. James Island, however, the level (30 ng/

ampoule) was below the Quantitation Level (Appendix A), 

that would have allowed an ambient water concentration 

estimate to be made. The location of this POCIS adjacent to 

Great St. James, would make a connection to the Tutu Wellfi eld Superfund Site appear unlikely, due to the distance 

from the Superfund site, along with the lack of detections 

in the POCIS deployed in Turpentine Gut and Mangrove 

Lagoon, both of which are closer to the Superfund site. 

Summary and Conclusions

The deployment of fi ve POCIS in the STEER in February 

2012, and one in Turpentine Gut in May 2010 provides 

valuable information on the presence of stormwater contaminants that might be missed if sediments alone were 

sampled. Although Turpentine Gut is not within the 

boundaries of the STEER, this perennial stream drains most 

of the Jersey Bay watershed and empties into the STEER 

through Mangrove Lagoon. Although the deployment 

in Turpentine Gut occurred nearly two years before the 

POCIS were deployed in the STEER, the Turpentine Gut 

POCIS provides additional information on the presence 

of stormwater contaminants that can be transported to the 

STEER via Mangrove Lagoon. 

The analysis of the POCIS from both the STEER and 

Turpentine Gut resulted in the identifi cation of a number 

of stormwater contaminants, the majority at concentrations 

below USGS Reporting Limits. Stormwater contaminants 

including phthalate ester plasticizers, wood preservatives, 

personal care product/fragrance ingredients, plant sterols 

and a fecal indicator were present at levels that enabled 

estimates of ambient water concentrations. The stormwater 

contaminants detected appear fairly representative of the 

low- and mid-density urban development in the watershed. 

Signifi cantly, none of the nine pesticides, primarily agricultural use herbicides and insecticides, were detected in 

the POCIS. This would appear to refl ect the low level of 

agriculture in the watersheds surrounding the STEER and 

in St. Thomas in general. 

A total of 26 stormwater contaminants were detected at 

least once during the February 2012 deployment at the fi ve 

sites in the STEER, and estimates of ambient water concentrations could be made for nine of these stormwater contaminants. In Turpentine Gut, 31 contaminants were detected in 2010, and ambient water concentrations could be 

estimated for 17 of these contaminants. The higher number 

of contaminants present in Turpentine Gut, including those 

for which estimated ambient water concentrations could be 

made, might be expected given that Turpentine Gut drains 

the primary watershed that empties into the STEER. 

The most common contaminants identifi ed in the POCIS 

were the phthalate ester plasticizers DEP and DEHP. Both 

were present in the POCIS at all sites, and their concentrations were high enough to estimate ambient water 

concentrations. Both of these phthalates are ubiquitous 

environment contaminants, as they have had global use as 

plasticizers in industry and in the home. The estimated water concentration of DEHP in Turpentine Gut (1,100 ng/L) 

was above a chronic water quality criteria, and was the 

only stormwater contaminant found to be above an available water quality criteria. Both DEHP and DEP have been 

identifi ed as endocrine disruptors. 

The wood preservative para-cresol was found in Turpentine 

Gut at an estimated concentration of 520 ng/L. This compound was also present but below the Reporting Limit at all 

sites in the STEER, indicating possible widespread use. 

Bromoform, a natural byproduct of algal metabolism in 

marine environments, and byproduct of drinking water or 

wastewater chlorination, was present in quantifi able levels 

at all sites in the STEER, but not in Turpentine Gut. This 

was somewhat surprising, and suggests that the bromoform 

found in the STEER may be natural, and related to algal 

metabolism. All estimated concentrations were below 

established water quality criteria.

 

A number of fragrance components were also detected in 

the STEER and in Turpentine Gut. Acetophenone, a fra-
Summary and Conclusions

14

STEER Stormwater Contaminants Report

grance used in detergents and in cigarettes, was detected in 

Turpentine Gut, and was present at all sites in the STEER, 

but concentrations could not be estimated as they were below the Reporting Limit. Indole was detected in the POCIS 

deployed in Benner Bay. The fragrance ingredients camphor and galaxolide were also found at quantifi able levels 

in Turpentine Gut. Other fragrance compounds including 

benzophenone, d-limonene and tonalide were present but 

below the Reporting Limit at all sites. Other personal care 

products detected included the insect repellent DEET (n,ndiethyltoluamide), methyl salicylate (liniment), and menthol (decongestant). 

Finally, the animal/plant sterol cholesterol was detected 

above the Reporting Limit at all but one site in the STEER 

and also in Turpentine Gut. The fecal indicator skatol was 

detected in Turpentine Gut. A second fecal indicator 3-beta 

coprostanol was detected in Turpentine Gut but below the 

Reporting Limit. 

The POCIS passive water samplers represent a fairly new 

technology used by NOAA’s National Centers for Coastal 

Ocean Science along with project partners. The use of 

POCIS provides the opportunity to assess the presence of 

water soluble chemical contaminants in coral reef environments. 
Literature Cited

15

STEER Stormwater Contaminants Report

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D.T. Getting, J.P. Goddard, and S.E. Manahan. 2004. 

Development of a passive, in situ, integrative sampler for 

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Alvarez, D.A., W.L. Cranor, S.D. Perkins, V.L. Schroeder, 

S. Werner, E.T. Furlong, and J. Holmes. 2008. Investigation of organic chemicals potentially responsible for 

mortality and intersex in fi sh of the North Fork of the 

Shenandoah River, Virginia, during spring of 2007: U.S. 

Geological Survey Open-File Report 2008–1093, 16 p.

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Alvarez, D.A., K.A. Maruya, N.G. Dodder, W. Lao, E.T. 

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Bargar, T.A., V.H. Garrison, D. Alvarez, and K. Echols. 

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Cólon, I., D. Caro, C. J. Bourdony, and O. Rosario. 2000. 

Identifi cation of phthalate esters in the serum of young 

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Francy, D.S., A. M. Gifford, and R. A. Darner. 2003. 

Escherichia coli at Ohio Bathing Beaches - distribution, 

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phthalates DEHP, BBP, and DINP, but not DEP, DMP, or 

DOTP, alters sexual differentiation of the male rat. Toxicological Science 58(2): 350-365. 

Island Resources Foundation (IRF). 1993. Mangrove 

Lagoon/Benner Bay Area of Particular Concern (APC) and 

Area for Preservation and Restoration (APR) Management 

Plan: a comprehensive analytic study. Prepared by Island 

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Lawrence, S.J., and LaFontaine, J.H. 2010. Occurrence of 

organic wastewater-indicator compounds in urban streams 

of the Atlanta area, Georgia, 2003–2006: U.S. Geological 

Survey Scientifi c Investigations Report 2010–5209, 113pp.

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Masoner, J.R., and S. L. Mashburn. 2004. Water quality and possible sources of nitrate in the Cimarron Terrace 

Aquifer, Oklahoma, 2003. Scientifi c Investigations Report 

2004–5221. 60pp. 

Nemeth, D. and R. Platenberg. 2007. Diversity of freshwater fi sh and crustaceans of St. Thomas: watersheds and 

its relationship to water quality as affected by residential 

and commercial development. WRRI Project 2006VI73B. 

Division of Fish and Wildlife, Department of Planning and 

Natural Resources, St. Thomas. 28 pp. 

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 

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Palmer, C. J., and C. J. Reason. 2009. Relationships of 

surface bromoform concentrations with mixed layer depth 

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Cycles, 23, GB2014, doi:10.1029/2008GB003338
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Sánchez-Avila, J., R. Tauler, and S. Lacorte. 2012. Organic micropollutants in coastal waters from NW Mediterranean Sea: sources distribution and potential risk. Environment International 46:50-62. 

Singh, S.P., A. Azua, A. Chaudhary, S. Khan, K.L. Willett, 

and P.R. Gardinali. 2010. Occurrence and distribution of 

steroids, hormones and selected pharmaceuticals in South 

Florida coastal environments. Ecotoxicology 19:338-350. 

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Noori, J.P. Oriol, J. Pierce, R. Platenberg, S. Romano, D. 

Russo, and C. Settar. 99 pages.

U.S. Department of Human Health and Services (USDHHS). 2011. Report on carcinogens. Twelfth edition. U.S. 

Department of Health and Human Services Public Health 

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17Appendices

STEER Stormwater Contaminants Report

Appendix A. Raw data from deployment of POCIS in five locations in the STEER, February 2012. 

Mangrove Lagoon Benner Bay Rotto Cay Cowpet Bay Saint James Quantitation Level

 Compound ng/ampoule ng/ampoule ng/ampoule ng/ampoule ng/ampoule ng/ampoule

1,4-Dichlorobenzene 25.8 LQL 20.3 16.3 20.9 128

1-Methylnapthalene LQL LQL LQL LQL 8.1 64

2,6-Dimethylnapthalene LQL LQL LQL LQL LQL 64

2-Methylnapthalene 9.85 12.9 8.93 LQL 12.6 64

3,4-Dichlorophenyl isocyanate (m) LQL LQL LQL LQL LQL 1020

3-Beta-coprostanol (m) LQL LQL LQL LQL LQL 512

4-Cumylphenol (m) LQL LQL LQL LQL LQL 64

4-n-Octylphenol (m) LQL LQL LQL LQL LQL 32

4-Tert-octylphenol LQL LQL LQL LQL LQL 32

5-Methyl-1H-benzotriazole LQL LQL LQL LQL LQL 512

Acetophenone 91.2 86.3 92.3 79.5 71.5 128

Anthracene LQL LQL LQL LQL LQL 32

Anthraquinone (m) LQL LQL LQL LQL LQL 64

Atrazine LQL LQL LQL LQL LQL 256

Benzo(a)pyrene LQL LQL LQL LQL LQL 32

Benzophenone 45.2 58 36.7 32.4 44.6 128

Beta-sitosterol (m) 962 883 1340 728 455 1020

BHA (m) LQL LQL LQL LQL LQL 256

Bisphenol A (m) LQL LQL LQL LQL LQL 64

Bromacil LQL LQL LQL LQL LQL 256

Bromoform 1180 438 1220 844 840 256

Caffeine LQL LQL LQL LQL LQL 128

Camphor LQL LQL LQL LQL LQL 128

Carbaryl (m) LQL LQL LQL LQL LQL 128

Carbazole LQL LQL LQL LQL LQL 32

Chlorpyrifos LQL LQL LQL LQL LQL 512

Cholesterol (m) 481 2350 1180 1710 808 512

Cotinine (m) LQL LQL LQL LQL LQL 128

Cumene 25.8 27.4 27 24.9 13.2 64

Diazinon LQL LQL LQL LQL LQL 512

Dichlorvos LQL LQL LQL LQL LQL 128

Diethyl phthalate 317 301 236 328 384 64

Diethylhexyl phthalate 170 146 144 183 658 64

d-Limonene 89.1 148 92.2 116 137 256

Ethanol,2-butoxy-,phosphate LQL LQL LQL LQL LQL 1020

Ethyl citrate LQL LQL LQL LQL LQL 64

Fluoranthene LQL LQL LQL LQL LQL 32

Galaxolide (HHCB) 15.4 LQL 16.1 15.9 12.8 62.7

Note: Quantitation level based on lowest standard; two POCIS disks were deployed at each site; m, highly variable compound; LQL, not detected above quantitation 

level; all results below quantitation level are considered estimated. Surrogates are internal standards used to measure extraction efficiency.
18Appendices

STEER Stormwater Contaminants Report

Appendix A. Raw data from deployment of POCIS in five locations in the STEER, February 2012 (continued). 

NWQL spike NWQL blank POCIS field blank POCIS Fab Blank

 Compound % Recovery ng/ampoule ng/ampoule ng/ampoule

1,4-Dichlorobenzene 84.8 LQL 75.6 LQL

1-Methylnapthalene 76.97 LQL 4.58 LQL

2,6-Dimethylnapthalene 83.35 LQL LQL LQL

2-Methylnapthalene 83.87 LQL 8.87 9.65

3,4-Dichlorophenyl isocyanate (m) 64.62 LQL LQL LQL

3-Beta-coprostanol (m) 85.38 LQL LQL LQL

4-Cumylphenol (m) 100.62 LQL LQL LQL

4-n-Octylphenol (m) 88.12 LQL LQL LQL

4-Tert-octylphenol 88.28 LQL LQL LQL

5-Methyl-1H-benzotriazole 97.18 LQL LQL LQL

Acetophenone 87.29 LQL 55 24.7

Anthracene 81.35 LQL LQL LQL

Anthraquinone (m) 97.77 LQL LQL LQL

Atrazine 83.95 LQL LQL LQL

Benzo(a)pyrene 76.24 LQL LQL LQL

Benzophenone 87.86 LQL 22.8 23.4

Beta-sitosterol (m) 85.95 LQL LQL LQL

BHA (m) 85.33 LQL LQL LQL

Bisphenol A (m) 88.15 LQL LQL LQL

Bromacil 89.92 LQL LQL LQL

Bromoform 83.79 LQL LQL LQL

Caffeine 89.39 LQL LQL LQL

Camphor 85.15 LQL LQL LQL

Carbaryl (m) 89.84 LQL LQL LQL

Carbazole 78.75 LQL LQL LQL

Chlorpyrifos 78.13 LQL LQL LQL

Cholesterol (m) 86.47 LQL 106 LQL

Cotinine (m) 97.82 LQL LQL LQL

Cumene 70.75 LQL LQL LQL

Diazinon 79.61 LQL LQL LQL

Dichlorvos 96.23 LQL LQL LQL

Diethyl phthalate 88.47 LQL 148 87.6

Diethylhexyl phthalate 86.56 LQL 189 80

d-Limonene 88.84 LQL 114 65.8

Ethanol,2-butoxy-,phosphate 81.11 LQL LQL LQL

Ethyl citrate 93.47 LQL LQL LQL

Fluoranthene 74.41 LQL LQL LQL

Galaxolide (HHCB) 76.42 LQL 7.74 LQL

Note: Quantitation level based on lowest standard; two POCIS disks were deployed at each site; m, highly variable 

compound; LQL, not detected above quantitation level; all results below quantitation level are considered estimated. 

Surrogates are internal standards used to measure extraction efficiency; NWQL, National Water Quality Laboratory.
19Appendices

STEER Stormwater Contaminants Report

Appendix A. Raw data from deployment of POCIS in five locations in the STEER, February 2012 (continued). 

Mangrove Lagoon Benner Bay Rotto Cay Cowpet Bay Saint James Quantitation Level

 Compound ng/ampoule ng/ampoule ng/ampoule ng/ampoule ng/ampoule ng/ampoule

Indole LQL 78.3 LQL 22.2 LQL 64

Isoborneol LQL LQL LQL LQL LQL 128

Isophorone LQL LQL LQL LQL LQL 64

Isoquinoline LQL LQL LQL LQL LQL 64

Menthol LQL 698 LQL LQL LQL 512

Metalaxyl LQL LQL LQL LQL LQL 256

Methyl salicylate 51.8 44.3 43 38.7 29.6 128

Metolachlor LQL LQL LQL LQL LQL 64

N,N-diethyltoluamide (DEET) 99 48.4 16.4 LQL LQL 64

Naphthalene 20.1 15.8 17.5 17.9 20.2 32

NPEO1 (m) LQL LQL LQL LQL LQL 513

NPEO2 (m) LQL 584 357 368 334 1020

OPEO1 (m) LQL LQL LQL LQL LQL 63.4

OPEO2 (m) LQL LQL LQL LQL LQL 87

Para-cresol 32.6 70.3 36.2 34.9 37.5 128

Para-nonylphenol (m) LQL LQL LQL LQL LQL 455

PBDE-47 (m) LQL LQL LQL LQL LQL 67.8

Pentachlorophenol (m) LQL LQL LQL LQL LQL 512

Phenanthrene LQL LQL 9.15 11.1 9.68 32

Phenol 794 1320 60.3 151 102 128

Prometon LQL LQL LQL LQL LQL 256

Pyrene LQL LQL LQL LQL 4.51 32

Skatol LQL LQL LQL LQL LQL 64

Stigmastanol (m) LQL 321 233 LQL 220 512

Tetrachloroethylene (m) LQL LQL LQL LQL 30 256

Tonalide (AHTN) LQL LQL LQL LQL LQL 62.7

Tri(2-chloroethyl)phosphate LQL LQL LQL LQL LQL 256

Tri(dichlorisopropyl)phosphate LQL LQL 45.4 LQL LQL 512

Tributylphosphate LQL LQL LQL LQL LQL 64

Triclosan LQL LQL LQL LQL LQL 512

Triphenyl phosphate LQL LQL LQL LQL LQL 128

Surrogates

decafluorobiphenyl 89.5 95.05 90.86 89.84 96.48

d9-Caffiene 100.62 103.29 101.98 93.73 105.54

d10 - fluoranthene 97.79 96.99 94.39 90.65 103.24

d16 bisphenol A 106.37 108.04 105.33 42.89 103.68

Note: Quantitation level based on lowest standard; two POCIS disks were deployed at each site; m, highly variable compound; LQL, not detected above quantitation 

level; all results below quantitation level are considered estimated. Surrogates are internal standards used to measure extraction efficiency.
20Appendices

STEER Stormwater Contaminants Report

Appendix A. Raw data from deployment of POCIS in five locations in the STEER, February 2012 (continued). 

NWQL spike NWQL blank POCIS field blank POCIS Fab Blank

 Compound % Recovery ng/ampoule ng/ampoule ng/ampoule

Indole 88.95 LQL LQL LQL

Isoborneol 77.04 LQL LQL LQL

Isophorone 90.89 LQL LQL LQL

Isoquinoline 94.51 LQL LQL LQL

Menthol 89.43 LQL LQL LQL

Metalaxyl 90.15 LQL LQL LQL

Methyl salicylate 93.49 LQL 24 LQL

Metolachlor 85.22 LQL LQL LQL

N,N-diethyltoluamide (DEET) 96.6 LQL LQL LQL

Naphthalene 81.79 LQL 11.2 9.77

NPEO1 (m) 108.93 LQL LQL LQL

NPEO2 (m) 97.71 LQL LQL LQL

OPEO1 (m) 87.52 LQL LQL LQL

OPEO2 (m) 95.86 LQL LQL LQL

Para-cresol 89.66 LQL LQL LQL

Para-nonylphenol (m) 73.82 LQL LQL LQL

PBDE-47 (m) 84.19 LQL LQL LQL

Pentachlorophenol (m) 100.12 LQL LQL LQL

Phenanthrene 78.45 LQL 6.34 8.38

Phenol 87.96 LQL 45.9 33.6

Prometon 89.04 LQL LQL LQL

Pyrene 82.83 LQL LQL LQL

Skatol 86.53 LQL LQL LQL

Stigmastanol (m) 89.9 LQL LQL LQL

Tetrachloroethylene (m) 57.1 LQL LQL LQL

Tonalide (AHTN) 84.5 LQL LQL LQL

Tri(2-chloroethyl)phosphate 77.44 LQL LQL LQL

Tri(dichlorisopropyl)phosphate 84.29 LQL LQL LQL

Tributylphosphate 92.18 LQL LQL LQL

Triclosan 89.77 LQL LQL LQL

Triphenyl phosphate 83.65 LQL LQL 17.2

Surrogates

decafluorobiphenyl 92.53 92.17 91.2 96.71

d9-Caffiene 95.65 79.8 101.74 100.9

d10 - fluoranthene 95.59 94.81 100.45 103.04

d16 bisphenol A 102.05 56.4 102.35 94.5

Note: Quantitation level based on lowest standard; two POCIS disks were deployed at each site; m, highly variable 

compound; LQL, not detected above quantitation level; all results below quantitation level are considered estimated. 

Surrogates are internal standards used to measure extraction efficiency; NWQL, National Water Quality Laboratory.
21Appendices

STEER Stormwater Contaminants Report

Appendix B. Raw data from deployment of POCIS in Turpentine Gut in May 2010. 

Report Level

Turpentine Gut based on lowest standard (0.16) Lab Solution Spike Lab procedure Blank Equipment Blank Field Blank

 Compound ng/ampoule ng/ampoule % Recovery ng/ampoule ng/ampoule ng/ampoule

1,4-Dichlorobenzene ++ 130 96.2 ++ ++ ++ 

1-Methylnapthalene ++ 64 92.2 ++ ++ ++ 

2,6-Dimethylnapthalene ++ 64 93.6 ++ ++ ++ 

2-Methylnapthalene ++ 64 94.5 ++ ++ ++ 

3,4-Dichlorophenyl isocyanate ++ 1000 45.3 ++ ++ ++ 

3-Beta-coprostanol 220 510 85.7 ++ ++ ++ 

4-Cumylphenol ++ 64 104.5 ++ ++ ++ 

4-n-Octylphenol ++ 32 93.5 ++ ++ ++ 

4-Tert-octylphenol 130 32 83.5 ++ ++ ++ 

5-Methyl-1H-benzotriazole E 830 510 84.9 ++ ++ ++ 

Acetophenone 210 130 93.5 ++ ++ ++ 

Anthracene ++ 32 88.9 ++ ++ ++ 

Anthraquinone ++ 64 107.6 ++ ++ ++ 

Atrazine ++ 260 95.3 ++ ++ ++ 

Benzo(a)pyrene ++ 32 91.6 ++ ++ ++ 

Benzophenone 46 130 95.1 ++ 20 24

Beta-sitosterol 670 1000 98.2 ++ ++ ++ 

BHA ++ 260 89.1 ++ ++ ++ 

Bisphenol A 250 64 89.9 ++ U-Deleted U-Deleted

Bromacil ++ 260 94.7 ++ ++ ++ 

Bromoform ++ 260 93.1 ++ ++ ++ 

Caffeine ++ 130 95.1 ++ 12 ++ 

Camphor 200 130 93.2 ++ ++ ++ 

Carbaryl ++ 130 93.6 ++ ++ ++ 

Carbazole ++ 32 96.7 ++ ++ ++ 

Chlorpyrifos ++ 510 93.6 ++ ++ ++ 

Cholesterol 1600 510 87.9 ++ ++ ++ 

Cotinine ++ 130 96.2 ++ ++ ++ 

Cumene ++ 64 94.1 ++ ++ ++ 

Diazinon ++ 510 89.3 ++ ++ ++ 

Dichlorvos ++ 130 85.4 ++ ++ ++ 

Diethyl phthalate 480 64 87.1 ++ 700 120

Diethylhexyl phthalate 3000 64 91.5 ++ 3300 3500

d-Limonene 160 260 101.4 ++ ++ ++ 

Ethanol,2-butoxy-,phosphate 1600 1000 89.0 ++ ++ ++ 

Ethyl citrate ++ 64 90.0 ++ ++ ++ 

Fluoranthene ++ 32 98.5 ++ 5.4 4.8

Galaxolide (HHCB) 250 63 93.4 ++ 12 9.6

Note: Reporting level based on lowest standard; two POCIS disks were deployed at each site; ++, not detected above reporting leve; E, estimated due to some 

chromatographic interference; <, raised report level - chromatographic interference; U-deleted - bisphenol A due to uncertainty of recovery due to no labeled bisphenol A 

surrogate recovery. Surrogates are internal standards used to measure extraction efficiency.
22Appendices

STEER Stormwater Contaminants Report

Appendix B. Raw data from deployment of POCIS in Turpentine Gut in May 2010 (continued). 

Report Level

Turpentine Gut based on lowest standard (0.16) Lab Solution Spike Lab procedure Blank Equipment Blank Field Blank

 Compound ng/ampoule ng/ampoule % Recovery ng/ampoule ng/ampoule ng/ampoule

Indole 620 64 95.3 ++ ++ ++ 

Isoborneol ++ 130 86.8 ++ ++ ++ 

Isophorone < 71 64 82.8 ++ ++ ++ 

Isoquinoline ++ 64 90.5 ++ ++ ++ 

Menthol 340 510 101.0 ++ ++ ++ 

Metalaxyl ++ 260 99.3 ++ ++ ++ 

Methyl salicylate 62 130 98.0 ++ 36 24

Metolachlor ++ 64 94.9 ++ ++ ++ 

N,N-diethyltoluamide (DEET) 1500 64 96.9 ++ 10 ++ 

Naphthalene 30 32 93.6 ++ ++ ++ 

NPEO1 ++ 510 107.9 ++ ++ ++ 

NPEO2 ++ 1000 97.3 ++ ++ ++ 

OPEO1 < 170 63 81.4 ++ ++ ++ 

OPEO2 130 87 63.4 ++ ++ ++ 

Para-cresol 3000 130 98.6 ++ ++ ++ 

Para-nonylphenol ++ 460 82.7 ++ ++ ++ 

PBDE-47 ++ 68 89.7 ++ ++ ++ 

Pentachlorophenol 81 510 97.5 ++ ++ ++ 

Phenanthrene ++ 32 93.8 ++ 9.5 9.2

Phenol 210 130 102.7 ++ ++ ++ 

Prometon ++ 260 96.1 ++ ++ ++ 

Pyrene ++ 32 96.4 ++ 3.1 2.8

Skatol 75 64 95.7 ++ ++ ++ 

Stigmastanol 280 510 89.7 ++ ++ ++ 

Tetrachloroethylene ++ 260 75.4 ++ ++ ++ 

Tonalide (AHTN) 44 63 91.7 ++ ++ ++ 

Tri(2-chloroethyl)phosphate 200 260 85.2 ++ ++ ++ 

Tri(dichlorisopropyl)phosphate 480 510 93.5 ++ ++ ++ 

Tributylphosphate 72 64 71.8 ++ ++ ++ 

Triclosan ++ 510 91.1 ++ ++ ++ 

Triphenyl phosphate ++ 130 96.0 ++ ++ ++ 

Method Surrogates

DECAFLUOROBIPHENYL 87.37 92.6 83.74 84.64 95.72

d9-CAFFEINE 104.29 92.5 79.11 110.76 107.68

d10-FLUORANTHENE 99.26 96.0 92.75 117.03 110.74

d16-BISPHENOL A 114.85 87.8 60.65 0 0

Note: Reporting level based on lowest standard; two POCIS disks were deployed at each site; ++, not detected above reporting leve; E, estimated due to some 

chromatographic interference; <, raised report level - chromatographic interference; U-deleted - bisphenol A due to uncertainty of recovery due to no labeled bisphenol A 

surrogate recovery. Surrogates are internal standards used to measure extraction efficiency.

STEER Stormwater Contaminants Report

Introduction

24

The mission of the National Centers for Coastal Ocean Science is to provide managers 

with scientifi c information and tools needed to balance society’s environmental, social and 

economic goals. For more information, visit: http://www.coastalscience.noaa.gov/. 

U.S. Department of Commerce

Rebecca Blank, Deputy Secretary

National Oceanic and Atmospheric Administration

Kathryn Sullivan, Acting Under Secretary for Oceans and Atmosphere

National Ocean Service

Holly Bamford, Assistant Administrator for Ocean Service and Coastal Zone Management