Page 8

Constant Contaminant Input
with migration

at NYS.

B

Decreasing Contaminant Input
without migration

Decreasing Contaminant Input
with migration

| |

Contaminants Contamination

in Flounder

Contaminants
in Lobster

Spring Fall, = Spring — Fall.

Figure 3.

Spring Fal

Spring Fatt Spring Fallt Spring Fall

Hypothetical contaminant loadings and resulting contaminant burdens in winter flounder and American lobster in the New

York Bight apex under different migration assumptions. (See text for detail.)

served. Winter flounder migrations have been followed in
this study (Valdes 1988). The fish leave the estuary for the
New York Bight apex in spring and return to the estuary in
winter. Thus, lobsters arriving in the apex are likely to have
relatively low contaminant burdens and be entering a more
contaminated environment, while the opposite is likely the
case for flounder.

We have constructed a hypothetical model based on
these considerations (Figure 3), assuming that contaminant
body burdens are functions of: (1) length of exposure time,
(2) level of environmental contamination, and (3) species-
specific elimination rate. In Figure 3A, we show the
hypothetical body burdens for the case where environmental
contamination in the New York Bight apex is constant.
Variation in body burdens over time would then fluctuate as
a result of the relative exposure intensity which is assumed
to be highest in the estuary for the winter flounder and
highest in the apex for the lobster.

Our objective in this study was to document environ-
mental and biological conditions in and around the “12-
mile” dumpsite related to the cessation of sewage sludge
dumping. Therefore, we also sampled across another gradi-
ent: the presumed temporal decrease in environmental con-
tamination following cessation of dumping. To help under-
stand how this gradient may be expected to affect contami-
nant burdens in flounder and lobsters in the New York Bight
apex, two more conditions are included in our model. Inthe
middle panel (Figure 3B), we show the expected effect on
contaminant burdens of decreasing environmental contami-
nation if the animal were not free to migrate (for example if
they were confined in cages). In the final panel (Figure 3C),
we combine the expected effects of migration and decreas-
ing environmental contamination. Under conditions of
decreasing environmental exposure, the contamination in
lobster would be expected to decrease, but since the flounder
are still exposed to high concentrations in the estuary,

decreases in their contaminant burdens would be expected
to be minimal.

In light of the expected trends shown in Figure 3, we
note several trends in the data of this study that, while not
statistically significant, are interesting. The lobster data
(Table 5) for most contaminants at station NY | | are consis-
tent with both the pattern expected as a consequence of
migration and that from pollution abatement. Lower values
of contaminant concentration at the time of the first sam-
pling in spring 1987 may be due to the shoreward migration
of offshore animals with low body burdens. Low values at
the end of the period covered by this paper may be due to the
cessation of dumping.

For winter flounder, the highest values for most PCBs
(Table 5) were found in the June 1987 samples, as might be
expected because of one or both of two compounding
reasons. Contaminant loading at the “12-mile” site was at
the highest level (of the three sampling periods; see Figure
2) in June 1987, and animals migrating out of the estuary in
spring likely had elevated body burdens, However, in
contrast to the observations on lobsters, the lowest concen-
trations were not found in the samples collected the longest
time after cessation (November 1988), but in November
1987 instead. It is possible that the proximity of station NY6
to the Hudson-Raritan Estuary, rather than its closeness to
the “12-mile” dumpsite, may contribute to the observation
that major organic contaminants are consistently higher in
animals from station NY6 than station NY 11. Future analy-
ses of specimens (including animals from station R2; see
Figure |) will help to resolve this question by increasing the
temporal and spatial distribution of observations.

There was a significant interspecific difference in PCB
content which we assumed for the construction of the model
might be due to species-specific differential net elimination
rates. Similarly, in the few data for PAH concentrations
(Table 5), values in flounder were all below the limit of.


Page iii

TABLE OF CONTENTS

Abstract .
Introduction
Methods ..

Sampling Design .

Analytical Methods .
Results ...
Discussion
Summary

Observations Requiring Additional Analyses and Evaluation ..
Acknowledgements .....
References Cited

LIST OF FIGURES

Figure 1. Location of stations sampled regularly during the “12-mile” dumpsite response study ....

Figure 2. Negotiated phaseout schedule for sewage dumping at the “12-mile” dumpsite,
including winter flounder and American lobster sampling periods ...

Figure 3. Hypothetical contaminant loadings and resulting contaminant burdens in winter flounder
and American lobster in the New York Bight apex under different migration assumptions ....

LIST OF TABLES

Table 1. Number of composites to be analyzed for organic contaminants according to the original sampling
design, on a station, species, and spawning condition basis
Table 2. Number of composites actually analyzed for organic contaminants on a species, sampling period,
and station basis ...
Table 3. Characteristics of specimens used for organic contaminant analysis on a species, station,
cruise/sampling period, and composite basis ....
Table 4. SIM ions used in the GC-MS analyses for PCBs .
Table 5. Concentrations of organic contaminants and lipid content on a species, cruise, and station basis ....
Table 6. Concentrations of selected organic contaminants, normalized by percent lipid content, on a species,
ctuise, and station basi:
Table 7. Detection limits of 2,3,
station basis .
Table 8. Concentrations of total PCBs on a species, composite, cruise, and station basis

, composite, cruise, and

‘Preceding page blank |


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Page 4

Table 3. Characteristics of specimens {i.e., animal no., length (mm), weight (g), and sex (M/F)] used for organic contaminant
analysis on a species, station, cruise/sampling period, and composite basis

Species Station Cruise No./ Composite Species Characteristics
Sampling Period No. ‘Animal Length Weight Sex
(no) (mm) () yr)
Winter NY6 KG 8706/ 1 2 300 - F
flounder Jun. 1987 3 335 - F
4 335 - F
8 222 153 F
i 235 177 F
2 1 257 - M
6 233 - M
7 220 133 M
9 340 594 F
10 266 228 F
KA 8711/ 1 1 252 205 F
Nov. 1987 3 222 125 F
9 344 419 F
i 266 241 M
13 273 255 F
2 5 220 130 F
6 234 160 F
10 334 430 M
12 306 410 F
16 245 173 F
KA 8811/ 1 3 252 180 F
Nov. 1988 4 260 215 F
10 245 196 F
21 206 105 M
26 288 315 M
2 Ss 296 318 F
7 278 270 F
8 253 225 M
22 275 290 F
28 277 280 F
NYIL KG 8706/ 1 1 300 - F
Jun. 1987 2 298 - F
12 210 : F
18 287 - F
19 288 - F
2 6 225 - F
7 203 - M
10 307 - F
17 315 : M
20 255 - M
American NY6 KA 8711/ 1 1 65 180 M
lobster Nov. 1987 3 74 220 M
4 46 95 -M
2 2 61 180 M
5 62 205 M
6 58 155 F
KA 8811/ 1 1 83 400 F
Nov. 1988 26 66 198 F
27 67 245 F
2 4 69 263 F
13 75 275 F
7 79 300 M


Page 1

ABSTRACT

Analyses for organic contaminants in the hepatic tissues of winter flounder (Pleuronectes americanus) and American
lobster (Homarus americanus) collected from the area of the “12-Mile” Sewage Sludge Dumpsite in the New York Bight
apex at various times during and after the phased cessation of dumping revealed two statistically significant results
(P<0.05). For each sampling period: (1) concentrations of polychlorinated biphenyls in flounder and lobster taken nearer
the dumpsite were higher than in those from a reference area, and (2) lobster values were higher than those for flounder._.

2)
‘

INTRODUCTION

The concentrations of polynuclear aromatic hydrocar-
bons (PAHs) and polychlorinated biphenyls (PCBs), along
with other anthropogenic contaminants, have been found to
be higher in the sediments of the Christiaensen Basin
(Figure 1) near waste dumpsites than at surrounding stations
in the New York Bight apex (Boehm 1982). There are
several routes by which contaminants enter the New York
Bight apex (Gross 1976). Sewage sludge from the New
York Metropolitan Area that was dumped (Figure 2) at the
“12-mile” site is the main focus of this study. (The recent
history of sewage sludge dumping is detailed below.) In
addition, sediment dredged from the New York Harbor
complex (about 10’ m? yr; Mueller et al. 1976) is dumped
at the dredge spoils site (Figure 1). Particularly relevant to
the present study are PCBs that have accumulated in the
sediments of the Hudson River and the harbor mainly as a
result of discharge from the General Electric plants at Ft.

Edward and Hudson Falls (Brown et al. 1985). In general, ~~ ;

concentrations of PCBs in dredged material from the harbor
complex range from nil to 10 mg/kg (Conner et al. 1979).
Moreover, estuarine outflow probably carries PCBs on
suspended sediment from the Hudson-Raritan Estuary, along
with other contaminants and nutrients (Mueller et al. 1976).
Finally, minor amounts of contaminants also enter the New
York Bight by atmospheric deposition (e.g., Gibson et al.
1979; Stanford and Young 1988). .

After over 60 years of dumping of sewage sludge at the
“12-mile” site (Figures 1 and 2), a phased cessation of
dumping began in March 1986 when a site more than 100
miles from New York was brought into use. From June 1986
to July 1987, dumping at the “12-mile” dumpsite was
conducted at a level of approximately 70-percent of the
precessation rate, and all dumping was phased out by
December 31, 1987. Termination of dumping provided a
unique opportunity to conduct a very-large-scale, environ-
mental perturbation experiment on the relation between
sediment biogeochemistry, benthic community structure,
and finfish distributions. The Northeast Fisheries Science
Center (NEFSC) instituted a program (Environmental Pro-
cesses Division, Northeast Fisheries Center 1988) to docu-
ment environmental and biological conditions in and around
this dumpsite as related to the cessation of sewage sludge
dumping. This paper reports data on organic contaminant
levels in livers of winter flounder (Pleuronectes americanus)

Tato"

O46 \ ny
\ Siew J
ons
ens
oo bas" 2,
“Christiansen Azg,
‘ays Basin NYE, om
ene
| sugge
JOumpsite:
wn
y nes
LEGEND
E> Fepieate
stations, ¢ aer20—
Broadscale 2m a
stations . M54
¥ avi \
Figure 1. Location of stations sampled regularly during the

“12-mile” dumpsite response study, (Stations in
small type were sampled less frequently to monitor
any contamination from proposed increases in
dredged-material dumping.)

and the hepatopancreas tissues of. ‘American lobster (Homarus
americanus) collected on three cruises between June 1987
and November 1988.

METHODS

SAMPLING DESIGN

Animals were collected by otter trawl fromthe NEFSC’s
research vessel Kyma over the course of two weeks during
the regular NEFSC surveys of the dumpsite area or in the
week thereafter. Specimens were measured and weighed
(except when sea conditions were too rough), and the sex
determined. Dissections were made under HEPA (high-
efficiency particulate air)-filtered air using dichlorometh-
ane-rinsed implements. The tissues were placed in
dichloromethane-cleaned jars with Teflon-lined screw caps
(from I-Chem Research, Hayward, California) and frozen at
-20°C.




Page 3

Table 1. | Number of composites to be analyzed for organic contaminants, according to the original sampling design, on a station,
species, and spawning condition basis
Station Winter Flounder American Lobster
Pre-spawn Post-spawn Pre-spawn Post-spawn
NY6 3 2 2 3
NY11 3 2 2 3
Table 2. | Number of composites actually analyzed for organic contaminants on a species, sampling period, and station basis
Species June 1987 November 1987 November 1988
NY6 NYI1 NY6 NY11 NY6 NY11
Winter flounder 2 2 - 2 -
American lobster - 2 2 2 2

containing 20 g of silica gel with 300 ml of hexane. The
eluant was concentrated to a final volume of 100 yl, and
sequentially analyzed by gas chromatography - mass spec-
trometry (GC-MS) for PAHs and PCBs. A quality control
(QC) matrix spike was prepared by adding known amounts
(1000 ng) of PAH and PCB analytes to lobster composite
No. 1 from June 1987. The recovery for PCB mixture
Aroclor 1260 was 76 percent, while recoveries for PAHs
ranged from 0 to 28 percent. In addition, QC blanks showed.
contamination with naphthalene, l-methy] naphthalene, and
2-methy! naphthalene. :

TCDD and TCDF Analyses

The extract remaining after the PAH and PCB analyses
was subjected to further purification as follows:

1. The analyte extract was diluted to 100 ml with hexane
and then washed with four 10-ml portions of concen-
trated sulfuric acid and finally with 10 ml of water. The
hexane layer was concentrated to 1 ml.

2. This extract was loaded on a column packed (from the
bottom) with 1 g of neutral silica gel, 2 g of 33-percent
NaOH-silica gel, 1 g of neutral silica gel, 20 g of 44-
percent sulfuric acid-silica gel, and 2 g of neutral silica
gel. The column was eluted with 150 ml of hexane, and
the eluant evaporated to near dryness.

3. Acolumn packed with 1.5 g of 10-percent silver nitrate-
silica was loaded with the hexane extract from step No.
2. It was eluted with 30 ml of hexane, and the eluant was
passed through a second column packed with 5 g of

basic alumina. The latter was washed with 50 ml of 50-
percent carbon tetrachloride-hexane. The chlorinated
dioxins and chlorinated dibenzofurans were eluted from
it with 60 ml of 50-percent dichloromethane-hexane,
and the eluant was evaporated to about 0.5 ml.

4. Apasteur pipette packed with 18-percent Carbopack C
on Celite 545 (1:4.5 mixture of Carbopack C, 80-100
mesh, and Celite 545, activated at 130°C for 6 hr) was
prewashed with 2 ml of toluene, 1 ml of 75:20:5
dichloromethane-methanol-benzene, | ml of 1:1 cyclo-
hexane-dichloromethane, and 2 ml of hexane. The
column was loaded with the hexane extract obtained
from step No. 3. It was then washed with two 1-ml
portions of hexane, 1 ml of 1:1 cyclohexane-
dichloromethane, and 1 ml of 75:20:5 dichloromethane-
methanol-benzene. The TCDD-TCDF fraction was
collected by elution with 2 ml of toluene and analyzed
by GC-MS.

GC-MS Analyses

The analytes were separated on a DB-S, fused-silica,
open-tubular capillary column (from J & W Scientific,
Folsom, California; 60-m x 0.25-mm LD. x 0.25-pm film
thickness) by using a Hewlett-Packard 5890 gas chromato-
gtaph. Helium was used as a carrier gas at a linear velocity
of 24 cm/sec, The column oven temperature was pro-
grammed from 150 to 340°C at a rate of 4°C/min. The
samples were introduced in a splitless injection mode. The
injector and the interface temperatures were each set at
250°C. The PAHs were analyzed by electron impact mass
spectrometry in the scan mode’ (total ion chromatogram),
while the PCBs (Table 4), 2,3,7,8-TCDD (m/z = 259, 320,
322), and 2,3,7,8-TCDF (m/z = 243, 304, 306) were ana-


Organic Contaminants

in Hepatic Tissues of Lobster
and Flounder at the New York Bight
''{2-Mile" Sewage Sludge Dumpsite:
1987-88

U. S. DEPARTMENT OF COMMERCE
National Oceanic and Atmospheric Administration
National Marine Fisheries Service
Northeast Region
Northeast Fisheries Science Center
Woods Hole, Massachusetts

July 1991



Page 6

Table 5. Concentrations (average of two composites) of organic contaminants (j1g/kg, wet weight) and lipid content (percent) on
a species, cruise, and station basis

Species Analyte KG 8706 KA 8711 KA 8811
NY6 NYil NY6 NY11 NY6 NY11

Winter flounder Lipid 23.0 34.0 18.0 22.6
Dichlorobipheny! 25 ND? ND 0.6
Trichlorobipheny! 42.2 18.8 13.6 24.1
Tetrachlorobiphenyl 194.5 95.1 58.4 113.6
Pentachlorobiphenyl 410.5 253.0 199.9 267.5
Hexachlorobipheny] 199.0 154.0 111.3 144.0
Heptachlorobipheny| 70.4 66.0 40.6 52.7
Octachlorobiphenyl 15.5 14.1 9.2 12.0
Nonachlorobiphenyl 2.2 6.0 19 2.0
Decachlorobipheny! ND 3.33 ND ND
Total PCBs 936.7 610.1 435.0 616.3
Fluoranthene ND ND ND ND
Pyrene ND ND ND ND

American lobster Lipid 49.9 24.1 31.2 35.7 34.8
Dichlorobipheny] 17.7 219 6.9 44 17
Trichlorobiphenyl 56.2 56.5 407 24.1 234.
Tetrachlorobiphenyl 247.5 327.0 256.5 130.7 118.2
Pentachlorobipheny] 549.0 721.5 624.5 340.5 284.0
Hexachlorobiphenyl 340.5 467.0 391.0 218.5 175.1
Heptachlorobipheny! 161.0 286.5 154.5 103.1 69.1
Octachlorobipheny1 39.0 37.7 39.2 26.7 19.2
Nonachlorobipheny! 12.9 22.4 12.0 5.7 3.8
Decachlorobipheny! 6.9 12.4 13.7 5.1 5.18
Total PCBs 1430.6 1952.8 1546.0 858.7 699.5
Fluoranthene ND 17.6 ND LP ND
Pyrene 50.9 7718 51.0 16.8 ND

© Consists of one value above the limit of detection and one measurement below which was taken as Zero.
© ND = not detected at the analytical and sample detection limit.

Table 6. Concentrations (average of two composites) of selected organic contaminants (g/kg, wet weight), normalized by percent
lipid content, on a species, cruise, and station basis

Species Analyte KG 8706 KA 8711 KA 8811
NY6 NY NY6_NYii Nyé NYil
Winter flounder Tetrachlorobiphenyl/lipid 8.5 33 3.0 49
Pentachlorobiphenyl/lipid 18.0 87 10.0 118
HexachlorobiphenyV/lipid 9.1 53 5.6 65
Fluoranthene/lipid ND* ND ND ND
Pyrene/lipid ND ND ND ND
American lobster Tetrachlorobiphenyl/lipid 61 16.0 83 39 3.6
Pentachlorobipheny//lipid 13.3 34.1 20.1 10.2 8.6
Hexachlorobiphenyl/lipid 83 211 12.6 63 53
Fluoranthene/lipid ND 14° ND 0.04% = ND
Pyrene/lipid 14 44 16 05 ND

© ND ~ nol detected at the analytical and sample detection limit.
© — Consists of one value above the limit of detection and one measurement below which was taken as zero,



Page 5

Table 3. Continued.
Species Station Cruise No.f Composite Species Characteristics
Sampling Period No. Animal Length Weight Sex
{no.) (mm) () (M/F)
American NY11 KG 8706/ 1 2 68 - M
lobster Jun. 1987 4 72 - F
9 81 - F
2 6 70 - F
8 a - M
20 70 - F
KA 8711/ 1 1 90- 250 M
Nov. 1987 2 100 335 F
4 70 301 M
2 3 79 295 M
Ss 73 288 F
KA 8811/ 1 10 81 370 M
Nov. 1988 11 59 170 M
25 61 114 F
2 6 70 260 F
12 77 350 F
30 68 275 M
Table 4. SIM ions used in the GC-MS analyses of PCBs
Group No.: 1 2 3 4 5
Start-stop (min): _5.00-15.94 15.94-21.14 21.14-24.35 24.35-31.41 31.41-38.00
m/z Dwell m/z Dwell m/z Dwell m/z Dwell m/z Dwell
152 50 186 50 254 sO 240 50 356 50
153 50 188 50 256 50 241 50 358 50
186 50 220 50 288 50 288 50 360 50
187 50 222 50 290 50 290 50 390 50
188 50 254 50 310 50 322 50 392 50
189 50 255 50 312 50 324 50 394 50
190 50 256 50 322 50 326 SO 424 50
220 50 258 50 323 50 356 50 425, 50
221 50 288 50 324 50 357 50 426 50
222 50 290 50 326 50 358 50 428 50
224 50 292 50 328 50 360 50 430 50
255 SO 294 50 357 50 362 50 432 50
256 50 310 50 358 50 391 50 462 50
258 50 312 50 360 50 392 50 464 50
290 50 324 50 362 50 394 50 466 50
292 50 326 50 392 50 396 50 496 50
294 50 328 50 394 50 398 50 498 50
310 50 358 50 396 50 428 50 499 50
312 50 360 50 398 50 430 50 500 50
362 50 432 50 502 50
lyzed by the electron impact mass spectrometry inthe select _ limit is defined as five times the variation of the baseline,

ion monitoring (SIM) mode by using a Hewlett-Packard
5996 mass selective detector with a direct capillary inter-
face. The relative electron multiplier voltage was 2500, and
the emission current was 300 A. The analytical detection

which is functionally equivalent to three times the mean
standard deviation. The limit of detection for each analyte
in each sample takes into account differences in the weight
of sample analyzed.


Page 2

Percent sewage sludge dumping

1986

Figure 2.

KG8706

KA8711

KA8811

12/15
|» End of 12-mile site use

J FMAMJJASONDJIFMAMJSJASOND JFMAMJJASOND

1987 1988

Negotiated phaseout schedule for sewage sludge dumping at the “12-mile” dumpsite, including winter flounder and

American lobster sampling periods. (Data modified from E. Santoro, U.S. Environmental Protection Agency, 26 Federal

Plaza, New York, NY 10278.)

The original sampling design (Table 1) called for the
analysis of a total of 20 composites of 20 g each. This weight
of tissue would require the tiver from about five flounder or
the hepatopancreas from about three lobsters. There were to
be 10 composites at each of two stations (NY6, contami-
nated; NY11, reference; see Figure 1). Within stations,
composites were to be allocated to consider spawning
condition (pre- and post-).

The number of composites to be analyzed was reduced
to 18 due to limited funds and difficulties in obtaining
animals as specified in the original sampling design (Table
1). For example, lobsters were not found at station NY6 in
June 1987, and flounder were not found at NY 11 in Novem-
ber 1988. In addition, the numbers of lobsters that could be
collectedat stations NY 6and NY 11 in November 1987 were
only six and five, respectively. We therefore based the final
scheme of analysis (Tables 2 and 3) on the following criteria:

1. All samples from station NY6 should be analyzed, on
the grounds that if contamination were occurring from
sewage sludge, it would probably be most evident at the
station closest to the dumpsite.

2. Time series at stations that include pre- and post-
cessation periods should be given priority, and
interstation comparisons should be secondary.

3. For a species, equal numbers of animals should be
included in each composite.

In the case of the November 1987 composite at station
NY11, criterion No. 3 was violated, but we considered it
preferable to uphold criterion No. 2.

ANALYTICAL METHODS
Analyte Extraction

A procedure based on a combination of three methods
(Environmental Protection Agency 1982, 1985, 1986) was
employed for the sequential analysis of PAHs, PCBs, 2,3,7,8-
tetrachlorodibenzodioxin (TCDD), and 2,3,7,8-
tetrachlorodibenzofuran (TCDF). Approximately 10 g (wet
weight) of the tissue homogenized with dry ice was spiked
with surrogates and internal standards, and then saponified
in 40-percent aqueous potassium hydroxide in a reflux
apparatus for 60 min. The solution was allowed to stand
overnight to ensure complete saponification. The solution
was then diluted with 50-percent aqueous ethanol and
extracted with one 25-ml portion and three 15-ml portions of
hexane. The combined hexane extract was washed with 10
ml of water to remove the excess base, and then evaporated
toa final volume of 1 ml.

PAH and PCB Analyses

To remove lipid-specific and other matrix interfer-
ences, the hexane extract was eluted through a column




Page 9

Table 8. Concentrations of total PCBs (g/kg, wet weight) on a species, composite, cruise, and station basis
Species Composite KG 8706 KA 8711 KA 8811
No. NY6 NYil NY6 NYIi NY6 NYIi
Winter flounder 1 622 329 159 760
2 1251 891 71 473
American lobster 1 1015 1407 1491 646 1049
2 1846 2499 1601 1071 350

detection, while in 11 of 20 lobster composites, PAHs were
detectable. This result is consistent with a biochemical
model which holds that PAHs are not found in finfish, but
are found in decapod crustaceans because of the less effi-
cient hepatic metabolic system of the latter (¢.g., Stegeman
1981).

Guidelines for TCDD concentrations as set by the Food
and Drug Administration (FDA) are 25 pg/kg for “limited”
consumption, and 50 pg/kg for no consumption (Miller
1983). Since the limit of detection in this study was so high
(190-2300 pg/kg; Table 7), and the values for all samples
were below the limits of detection, we cannot determine
from these data whether the fish and lobsters in the study
contained concentrations of TCDD above the guidelines.
However, the FDA action level for total PCBs in the edible
portion of fish and shellfish of 2 g/g (Food and Drug
Administration 1984) is applicable to our results. The
highest concentration of total PCBs we found was 2.5 ye/g
in lobster composite No. 2 from station NY6 in November
1987 (Table 8). This value is about equal to the lowest mean
values reported from Long Island Sound for the average of
20 lobsters (Chytalo 1989), and is well below the highest
mean concentration she reports of 7.08 ug/g. However,
composite No. 1 from the same sampling period and station
contained only 1.4 yg/g, resulting in an average of 1.95 pg/
g (Table 5) and suggesting the large variation among ani-
mals inourstudy. It appears, then, that the hepatopancreases
of some of the lobsters in the area of the “12-mile” sewage
sludge dumpsite were contaminated toa concentration above
the FDA action level.

SUMMARY

CONCLUSIONS

1. For each of the three sampling periods, PCB values in
both flounder and lobster were higher at the station
nearer the dumpsite (NY6) than at the station relatively
farther from the dumpsite (NY 11).

2. Foreach of the three sampling periods, PCB concentra-
tions in lobster were higher than in flounder.

OBSERVATIONS REQUIRING
ADDITIONAL ANALYSES AND
EVALUATION

1. Concentrations of organic contaminants in lobsters
were lowest in November 1988, perhaps associated
with the cessation of dumping.

2. Concentrations of organic contaminants in flounder
were highest in spring, perhaps associated with migra-
tions to the sampling area in the New York Bight apex
from the Hudson-Raritan Estuary.

3. Since detection limits were very high for 2,3,7,8-TCDD
(range of <0. 19 - <2.3 g/kg) and 2,3,7,8-TCDF (range
of <0.52 - <8.5 g/kg), more tissue or a more sensitive
analytical technique is required to discern spatial and
temporal changes in these contaminants.

4. Extraction andcleanup procedures for PAH trace analy-
sis from marine tissues need to be optimized to measure
compounds that were below the detection limit in these
samples.

5. PAH concentrations are consistent with a biochemical
model which holds that PAHs are not found in finfish,
but are found in decapod crustaceans because of the less
efficient hepatic metabolic system of the latter (e.g.,
Stegeman 1981).

ACKNOWLEDGEMENTS

We thank the captain and crew of the research vessel
Kyma and our colleagues in the Environmental Processes
Division’s Environmental Analysis Investigation for their
efforts in obtaining specimens, R. Pikanowski for statistical
assistance, and T. Finneran for dissections. The analyses
were conducted under Contract No. P50586 from the New
Jersey Department of Environmental Protection to the En-
vironmental Testing and Certification Corporation.


(continued from inside front cover)

68. MARMAP Surveys of the Continental Shelf from Cape Hatteras, North Carolina, to Cape Sable, Nova Scotia
(1984-87). Atlas No. 3. Summary of Operations. By John D. Sibunka and Myron J. Silverman. July 1989. iv + 197
p., 36 figs., 2 tables. NTIS Access. No. PB90-160656/AS.

69. The 1988 Experimental Whiting Fishery: A NMFS/Industry Cooperative Program. By Frank P. Almeida,
Thurston S. Bums, and Sukwoo Chang. August 1989. v + 16 p.,9 figs., 11 tables, 1 app. NTIS Access. No. PB90-
160664/AS.

70. Summer Distribution of Regulated Species on Georges Bank with Reference to the 1988 Experimental
Whiting Fishery. By Frank P. Almeida, Sukwoo Chang, and Thurston S. Burns. September 1989. v+ 25 p., 74 figs.,
1 table. NTIS Access. No. PB90-206525/AS.

71, Allocation of Statewide-Reported MRFSS Catch and Landings Statistics between Areas: Application to
Winter Flounder. By Frank P. Almeida. September 1989. v + 18p.,5 figs., 6 tables, 2 app. NTIS Access. No. PB90-
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72. Status of the Fishery Resources off the Northeastern United States for 1989. By Conservation and Utilization
Division, Northeast Fisheries Center. December 1989. iv + 110p., 50 figs., 93 tables. NTIS Access. No. PB90-170622/
AS.

73. Surface and Bottom Temperature Distribution for the Northeast Continental Shelf. By David G. Mountain
and Tamara J. Holzwarth. December 1989. iii + 32 p., 31 figs. NTIS Access. No. PB90-252172/AS.

74. Shell Disease of Crustaceans in the New York Bight. By C.J. Sindermann (chair.), F. Csulak (EPA coord.), T.K.
Sawyer (rapp.), R.A. Bullis, D.W. Engel, B.T. Estrella, E.J. Noga, J.B. Pearce, J.C. Rugg, R. Runyon, J.A. Tiedemann,
and R.R. Young. December 1989. vii + 47 p., 7 figs., 4 tables, 4 app. NTIS Access. No. PB90-195058/AS.

75. An Indexed Bibliography of Northeast Fisheries Center Publications and Reports for 1988. By Jon A. Gibson.
December 1989. iii + 32 p. NTIS Access. No. PB91-112912.

76. Finfish Maturity Sampling and Classification Schemes Used during Northeast Fisheries Center Bottom
Trawl Surveys, 1963-89. By Jay Burnett, Loretta O'Brien, Ralph K. Mayo, Jeffrey A. Darde, and Margot L. Bohan.
December 1989. iii+ 14 p., 11 tables, 1 app. NTIS Access. No. PB91-128389/AS.

77. Shell Disease among Red Crabs Inhabiting Submarine Canyons of the New York Bight. By Randall R. Young.
December 1989. iii+9 p., 18 figs., 5 tables. NTIS Access. No. PB90-194762/AS.

78. Seasonal Distribution Patterns of Commercial Landings of 45 Species off the Northeastern United States
during 1977-88, By Sukwoo Chang. October 1990. v+130 p., 246 figs. NTIS Access. No. PB91- 160846.

79. Contaminants in Sediment and Fish Tissue from Estuarine and Coastal Sites of the Northeastern United
States: Data Summary for the Baseline Phase of the National Status and Trends Program Benthic Surveillance
Project, 1984-1986. By Vincent S. Zdanowicz and Donald F. Gadbois. December 1990. x + 138p., 67 figs., 21 tables.
NTIS Access. No. PB92-147453/AS.

80. Distribution of Sexually Immature Components of 10 Northwest Atlantic Groundfish Species Based on
Northeast Fisheries Center Bottom Trawl Surveys, 1968-86. By Susan E. Wigley and Wendy L. L. Gabriel. January
1991. iv + 17 p., 23 figs., 3 tables. NTIS Access. No. PB92-101617.

81. Status of the Fishery Resources Off the Northeastern United States for 1990. By Conservation and Utilization
Division, Northeast Fisheries Center. January 1991. iv + 130 p., 50 figs., 82 tables. NTIS Access. No. PB91-213785.

82. Response of the Habitat and Biota of the Inner New York Bight to Abatement of Sewage Sludge Dumping:
Third Annual Progress Report--1989. By Anne L. Studholme, Merton C. Ingham, and Anthony Pacheco, eds.
February 1991. vi + 57 p., 74 figs., 20 tables, 1 app. NTIS Access. No. PB91-208199.


NOAA Technical Memorandum NMFS-F/NEC-83

This TM series is used for documentation and timely communication of preliminary results,
interim reports, or special purpose information, and has not undergone external scientific

review.

Organic Contaminants.
in Hepatic Tissues of Lobster -
and Flounder at the New York Bight
"412-Mile" Sewage Sludge Dumpsite:
1987-88

A. F. J. Draxler', Paul Hauge’, and Ashok D. Deshpande‘

‘National Marine Fisheries Service, Sandy Hook Lab., Highlands, NJ 07732
?New Jersey Dept. of Environmental Protection, Div. of Science & Research, Trenton, NJ 08625-0409

U. S. DEPARTMENT OF COMMERCE
Robert A. Mosbacher, Secretary

National Oceanic and Atmospheric Administration
John A. Knauss, Administrator

National Marine Fisheries Service
William W. Fox, Jr., Assistant Administrator for Fisheries
Northeast Region
Northeast Fisheries Science Center
Woods Hole, Massachusetts

July 1991

Lae


Recent issues in this series

53. Contaminants in Hudson-Raritan Estuary Water and Influence of Cold Storage upon Its Chemical
Composition. By Anthony Calabrese, Lawrence J. Buckley, and J. Christopher Powell. May 1988. vii + 37 p., 10 figs.,
11 tables. NTIS Access. No. PB88-225628/AS.

54. Epizootic Ulcerative Syndromes in Coastal/Estuarine Fish. By Carl J. Sindermann. June 1988. v + 37 p., 8 figs.,
1 table. NTIS Access. No. PB89-110803/AS.

55. A Plan for Study: Response of the Habitat and Biota of the Inner New York Bight to Abatement of Sewage
Sludge Dumping. By Environmental Processes Division, Northeast Fisheries Center. June 1988. iii + 34 p., 5 figs., 3
tables, 4 app. NTIS Access. No. PB89-100903/AS.

56. Characterization of the Middle Atlantic Water Management Unit of the Northeast Regional Action Plan. By
Anthony L. Pacheco, ed. July 1988. v + 322 p., 136 figs., 21 tables. NTIS Access. No. PB89-145262/AS.

57. An Analysis and Evaluation of Ichthyoplankton Survey Data from the Northeast Continental Shelf
Ecosystem. By Wallace G. Smith, ed. August 1988. xiii + 132 p., 53 figs., 12 tables, 1 app. NTIS Access. No. PB89-
122501/AS.

58. An Indexed Bibliography of Northeast Fisheries Center Publications and Reports for 1987. By Jon A. Gibson.
August 1988. iii + 20 p. NTIS Access. No. PB89-113013/AS.

59. Surveys of Breeding Penguins and Other Seabirds in the South Shetland Islands, Antarctica, January-
February 1987. By W. David Shuford and Larry B. Spear. September 1988. vii + 27 p., 14 figs., 1 table. NTIS Access.
No. PB89-141311/AS.

60. Survey of Antarctic Fur Seals in the South Shetland Islands, Antarctica, during the 1986-1987 Austral
Summer. By John L. Bengtson, Lisa M. Ferm, Tero J. Harkonen, Everett G. Schaner, and Brent S. Stewart. September
1988. vii + 8 p., 1 fig., 3 tables. NTIS Access. No. PB89-141303/AS.

61. Fish as Sentinels of Environmental Health. By Robert A. Murchelano. September 1988. iii + 16 p., 4 figs. NTIS
Access. No. PB89-139737/AS.

62. The Effects of Density Dependent Population Mechanisms on Assessment Advice for the Northwest Atlantic
Mackerel Stock. By W. J. Overholtz, S.A. Murawski, W.L. Michaels, and L.M. Dery. October 1988. v + 49 p.,7 figs.,
20 tables. NTIS Access. No. PB89-151948/AS.

63. Status of the Fishery Resources Off the Northeastern United States for 1988. By Conservation and Utilization
Division. October 1988. iii + 135 p., 51 figs., 52 tables. NTIS Access. No. PB89-130819/AS.

64. The Shell Disease Syndrome in Marine Crustaceans. By Carl J. Sindermann. February 1989. v + 43 p., 5 figs.,
2 tables. NTIS Access. No. PB89-162523/AS.

65. Stock Assessment Information for Pollock, Pollachius virens (L.), in the Scotian Shelf, Georges Bank, and Gulf
of Maine Regions. By Ralph K. Mayo, Stephen H. Clark, and M. Christina Annand. April 1989. vi + 14 p., 6 figs.,
14 tables. NTIS Access. No. PB90-120676/AS.

66. Guidelines for Estimating Lengths at Age for 18 Northwest Atlantic Finfish and Shellfish Species. By Judith
A. Pentilla, Gary A. Nelson, and John M. Burnett, III. May 1989. iii + 39p., 18 figs., 19 tables. NTIS Access. No., PB90-
120675/AS.

67. Response of the Habitat and Biota of the Inner New York Bight to Abatement of Sewage Sludge Dumping.

Second Annual Progress Report -- 1988. By Environmental Processes Division, Northeast Fishieries Center. July
1989. vii + 47 p., 39 figs., 11 tables, 3 app. NTIS Access. No. PB90-125444/AS.

(continued on inside back cover)

“e
n


Page 7

Table 7. Detection limits (ug/kg, wet weight) of 2,3,7,8-TCDD and 2,3,7,8-TCDF ona species, composite, cruise, and station basis
Species Analyte Composite KG 8706 KA 8711 KA 8811
No. NY6  NYil NY6NYI1 NY6  NYil
Winter flounder TCDD 1 <0.63 2 <2.10 <0.19
2 <0.93 <1.50 <1.80 <0.48
TCDF 1 <0.82 <3.30 <0.98 <0.52
2 <0.73 <0.81 <0.85 <0,52
American lobster. TCDD 1 <1.20 <0.65 <0.57 + <1.10
2 <0.60 <0.61 — <0.88 <1.00 — <2,30
TCDF 1 <0.82 <0.93 <0.59 <8.50  <0.78
2 <0.75 <084 — <0.88 <110  <1.80

Detection limit could not be calculated.

RESULTS

The concentrations of analytes aresummarized in Tables

5 and 6 as the average of each pair of composites. The

following trends can be discerned:

1. For any sampling period, nearly all PCB values were
higher in both flounder and Jobster from station NY6
than those from station NY 11. In a few instances, for
a few compounds present in concentrations near the
limit of detection, this was not the case. For example,
for nonachlorinated biphenyls in winter flounder col-
lected in June 1987, the station NY6 concentration was
determined as 2 pg/kg, while at station NY 11 it was 6
He/kg. Analytical and compositing variances probably
make these differences insignificant on a parametric
basis.

2. Fora given sampling period, all PCB concentrations in
lobster were higher than in flounder (with only one
exception in which they were equal).

3. Concentrations of PCBs in lobsters were approximately
equal during both sampling periods in 1987 (June and
November) and lowest in November 1988, 11 months
after dumping ceased at the “12-mile” site.

4. Concentrations of PCBs in flounder were highest dur-
ing the first sampling in spring 1987, and, in contrast to
lobsters, lowest in November 1987.

5. When contaminant concentrations are normalized to
lipid content (Table 6), the above results are basically
unchanged. However, the time-course decrease in
lobster PCB content (result No. 3 above) appears to be
more pronounced.

Wilcoxon's signed-rank test for comparing two popu-
lations using paired data indicates that results No. 1 and No.
2 above are statistically significant (P<0.05).

Since recoveries for PAHs were low and contamination
with certain compounds occurred in blanks, results for
PAHs must be considered tentative. In addition, most PAH
concentrations in lobster tissue and all PAH concentrations
in flounder livers were below the limit of detection of the
method. Those PAH values above the detection limit
(fluoranthene and pyrene) are included in Tables 5 and 6.
They follow the pattems of the PCB levels.

Inno sample was the dioxin or dibenzofuran concentra-
tion above the detection limit. For TCDD, detection limit
values ranged from <0.19 to <2.3 pg/kg; while for TCDF,
values ranged from <0,.52 to <8.5 g/kg (Table 7).

DISCUSSION

We found that contaminants in tissue were higher in
animals collected nearer the dumpsite than in animals from
the reference station farther from the dumpsite. This statis-
tically significant difference in contaminant burdens be-
tween the stations may reflect a rapid response to environ-
mental exposure. On the other hand, the result may be
complicated by our having sampled groups of animals with
different contaminant exposure histories due to differences
in migration at the two sites.

The migration of animals is expected to be one of the
largest sources of variation in the concentrations of contami-
nants in animal tissue from a given site. Since pollution
gradients in the New York Bight apex exist on the scale of
kilometers, a relatively uncontaminated animal could be
captured shortly after entering a contaminated site, or a
contaminated animal could entera relatively unpolluted area
and be captured. On a larger scale, lobsters migrate into the
New York Bight apex from offshore in the summer and
leave for the offshore areas when water temperature drops in
winter. This picture is compounded further by the existence
of a “coastal” population that is resident in the area (Uzmann
etal. 1977). Similarly, the seasonal migration patterns of
winter flounder should affect the contaminant burdens ob-


Page 10

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