Fish health and contamination study

[From the U.S. Government Printing Office, www.gpo.gov]

Fish Health and Contamination Study

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DEL USA Project Element 10

Funding Provided by the
Pennsylvania Coastal Zone Management Program

Delaware Estuary Use Attainability Project

Delaware River Basin Commission
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174 West Trenton, New Jersey
157
1988
C' March 1988

EXECUTIVE SUMMARY

A study of fish health (pathology) and fish tissue toxics was conducted in the
October 1986 to December 1987 period. Target fish (catfish family and white
perch) were collected at ten locations in Zones 2, 3 and 4 of the Delaware
Estuary. Individual fish and composites of fish were examined for general
health, pathogens, tumors and lesions, parasites, specific enzymatic
compounds, and organic and inorganic toxics. The results of the study
indicate that, while generally healthy, fish in the Delaware Estuary show the

affect of various environmental stresses and have accumulated various toxic

compounds in their tissue. Circumstantial evidence suggests that some toxic
compounds are causing fish health problems in selected individuals or species.
PCB concentrations were high enough in channel c atfish to question their
edibility from a human health viewpoint. Chlordane was found with PCBs but
not quantified. DDT metabolites were also identified in every fish tissue
sample but values did not exceed FDA Action Levels. Recommendations include
the need for a systematic approach for identifying fish contamination problems
and follow up studies.

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US Department of Commerce I
NOAA Coastal Services Center Library
223-'! South Hobson Avenue
Charleston, SC 29405-2413 1

ACKNOWLEDGMENTS

This report was the responsibility of the Delaware River Basin Commission,
Gerald M. Hansler, Executive Director. Richard Albert was the project
manager. The efforts of the following persons and organizations are grate-
fully acknowledged. In each case, assistance was either freely given or work
performed beyond the scope of any contract.

Funding: Primary funding for this study was obtained from the Pennsylvania
Department of Environmental Resources, Division of Coastal Zone Management
which administers coastal zone management funds provided by the Federal Office
of Ocean and Coastal Resource Management, National Oceanic and Atmospheric
Administration. The Contract and CZM Grant Task Numbers were ME #86247 and
86-PS.02 respectively. The Delaware River Basin Commission was the primary
contracting agency with sub-contracts awarded to Rutgers, The State
University, the New Jersey Department of Environmental Protection and the
Academy of Natural Sciences. Eric Conrad was the-PADER grant coordinator.

Study Design: The study was designed with assistance from the Delaware Bas in
Fish and Wildlife Cooperative, Ed Washuta with the NJDEP Division of Fish and
Game, Mike Kauffman with the Pennsylvania Fish Commission, Cindy Rice with the
U.S. Fish and Wildlife Service and Bruce E. Ruppel with the NJDEP Office of

Science and Research.

Fish Collection: John C. O'Herron, II, Rutgers University researcher, was the
primary fish collector. Fish were also collected by Cindy Rice, Dave Putnam,
Phil Edmonds and Joe Miller with the U.S. Fish and Wildlife Service, and Art
Lupine and Ed Washuta with the NJDEP Division of Fish and Game.

Fish Health Analyses: Ed Washuta, Bill Stansley, and D oug Roscoe with the
NJDEP, Division of Fish and Game, conducted the fish pathological and
toxicological studies.

Fish Tissue Analyses: Steve Friant, Senior Head Chemist with the Academy of
Natural Sciences, Division of Environmental Research, and his staff performed
the chemical analyses of the fish tissue composites.

Draft Report Review: Comments and suggestions on the draft report, received
from ten different state and federal agencies, resulted in improvements to the
final report.

TABLE OF CONTENTS

Page No.

Acknowledgments
Executive Summary

PART A - MAIN REPORT

Introduction

Purpose of Study
Relationship to Other DEL USA Elements 2
Study Design 3
Study Participants 3
Study Area 3
Study Approach 5
Selection of Target Fish 5
Selection of Sampling Locations 7

Fish Collection 8

Fish Health Analyses 9
Fish Tissue Analyses 10
Summary of Results 11

Fish Health 12

Fish Tissue Toxics 13

Overall Summary 14

Recommendations 18

PART B - DATA FROM FISH COLLECTION ACTIVITIES RUTGERS, THE STATE UNIVERSITY
Sampling Locations and Fish Collected I
Water Quality Data at Time of Fish Collection 5
Total Species and Abundance by Site 7

TABLE OF CONTENTS (contd.)

PART C FISH HEALTH DATA REPORT NEW JERSEY DEPARTMENT OF ENVIRONMENTAL

PROTECTION

Introduction C-1

Materials and Methods C-4

Results C-9

Gross Pathology C-9

Organosomatic Indices C-11
Bacteriology C-16
Parasitology C-16
Histopathology C-20
Liver Enzyme Assay C-30
Tissue Toxics Analyses C-37
Discussion C-48

General Condition C-48

Bacteriology C-48
Parasitology C-49
Idiopathic Lesions C-49
Summary C-53

Recommendations C-55

Literature Cited C-56

PART D - DATA REPORT OF ANALYSES OF DELAWARE RIVER FISH TISSUE FOR

TOXIC SUBSTANCES ACADEMY OF NATURAL SCIENCES

Introduction 1

Methods I

Results 3

Summary 4

Literature Cited 5

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I PART A - MAIN REPORT
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INTRODUCTION

The Delaware River Basin Commission, on behall of the lour basin states and
the federal government, initiated the Delaware Estuary Use Attainability (or
DEL USA) Project in 1986. Federal regulations require use attainability
analyses to be conducted on those water bodies where water quality standards
and designated uses are less than the federal w ater pollution goals. These
goals, contained in Section 101 (a)(2) of the Fe deral Clean Water Act
Amendments of 1987 (and preceding acts), call for water quality which provides
for the protection and propagation of aquatic like and recreation in and on
the water (i.e., the so-called fishable and swimmable goals respectively).
Also related is the national policy that the discharge of toxic pollutants in
toxic amounts be prohibited (Section 101 (a)(3)).

The objectives of use attainability studies, and the DEL USA Project in
particular, are (1) to address what constraints, if any, prevent the attain-
ment of the fishable and swimmable water quality goal and (2) to develop
programs for attaining these goals where feasible. Currently 40 miles of the
Delaware Estuary have designated user, which are less than fishable and 58
miles which are less than swimmable. Emerging as a concern as well are
questions about toxics and their impact on aquatic life and human health. The
two-year DEL USA Project is addressing these issues through a series of
technical and policy studies. These studies and the project approach are
outlined in the DEL USA Project Plan of Study dated May 1986.

PURPOSE OF STUDY

The Fish Health and Contamination Study was originally proposed for the
DEL USA Project by the Delaware Basin Fish and Wildlife Cooperative Technical
Committee. The objectives of the study were:

1. to provide needed data by location on fish pathological health (tumors,
pathogens, etc.);
2. to provide needed data on the concentrations of various toxicants in fish

tissue;

3. to develop, to the degree possible, inferences concerning the
relationships between toxicants and fish health; fish tissue toxicants and
toxics found in the estuary environment; and fish health and other water
quality factors; and
4. to provide information concerning the edibility of fish.

RRIATIONSHIP TO OTHER DEL USA PROJECT RIMMITS

The Fish Health and Contamination Study, while an independent study, was
designed to be an intrinsic part of the DEL USA Project. For example, various
DEL USA elements are addressing the attainment of fishable water quality
through the raising of dissolved oxygen standards. During the development of
the DEL USA Plan of Study, concerns were raised that fish health, fish tissue
toxics, and edibility considerations could jeopardize the potential fishery
benefits derived from improved dissolved oxygen levels. The Fish Health and
Contamination study is a response to this concern.

Because of the concern for toxics, the DEL USA Project conducted water and
sediment toxics surveys in May and June 1986 in conjunction with a DEL USA
study of sediment oxygen demand. The DEL USA report entitled 'Toxics Review
Study contains the results of these surveys. The water and sediment toxics
surveys and the Fish Health and Contamination Study were integrated by use of
common parameters and sampling locations. These studies and a third study,
the Chronic Toxicity Bioassay Study are the toxics elements of the DEL USA
Project and the precursor to future toxics work in the estuary.

The Fish Health and Contamination Study is also interrelated to the
fisheries-related elements of the DEL USA Project. The study adds to the
fishery data base used by the DEL USA Project (see DEL USA report Fish
Population Study) and will provide information to a DEL USA fish suitability
assessment. This latter effort will attempt to assess water quality, habitat,
toxics and other factors related to the restoration of fish in the estuary.
The assessment of potential constraints to the estuary's fisheries and an
assessment of the potential fisheries benefits of improved water quality will
assist the decision-making process, particularly if new, potentially costly
pollution controls are being considered.

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STUDY DESIGN

Study Participants
The Fish Health and Contamination Study was largely conducted with funds from
the Pennsylvania Department of Environmental Resources Coastal Zone Management
Program with a 20% match from the Commission. The study itself was developed
through consultation with personnel from the Pennsylvania Depart ment of
Environmental Resources Division of Coastal Zone Management, the New Jersey
Department of Environmental Protection (NJDEP) Division of Fish, Game and
Wildlife, the NJDEP-Office of Science and Research, the Pennsylvania Fish
Commission, the U.S. Fish and Wildlife Service, and the Philadelphia Academy
of Natural Sciences. Three subcontractors were used to conduct the study:
the NJDEP for fish pathology work, the Academy of Natural Sciences for fish
tissue toxics analyses and Rutgers University for fish collection. Fish were
also collected by U.S. Fish and Wildlife Service and NJDEP personnel. The
study was supervised and administered by DRBC staff.

Study Area
The study,area for the Fish Health and Contamination Study is a portion of the
Delaware Estuary, a tidal freshwater river in its upper sections and an
estuary in its lower reaches. It runs 85 miles f rom the head of tide at
Trenton, New Jersey (River Mile 133.4) to Liston Point, Delaware (R.M. 48.2).
For water quality management purposes the estuary is divided into four zones:
Zone 2 from Trenton (R.M. 133.4) to Philadelphia (R.M. 108.4); Zone 3 from
R.M. 108.4, past Philadelphia and Camden, to near the mouth of the Schuylkill
River (R.M. 95.0); Zone 4 to the junction of the Delaware, New Jersey and
Pennsylvania boundaries near Marcus Hook, Pennsylvania (R.M. 78.8); and Zone 5
to Liston Point, Delaware (R.M. 48.2). The Delaware Estuary is the world's
largest freshwater port and one of its great concentrations of heavy industry.
.The population of the estuary region is greater than 80% of the 50 states.

The reach of the estuary selected for study ran from the upstream end of
Burlington Island (R.M. 120) in Zone 2 to Eddystone, Pennsylvania (R.M. 84) in
Zone 4. This reach of the river has been intensely studied by other DEL USA
Project studies. Contained within the study reach are water supply intakes,
various large industrial and municipal discharges and other point and

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Figure 1. Location of Fish Collection Areas

A
1. B

2. Burl i
3. M. of Neshaminy Creek

4. Tacony-Palmyra Bridge

IV
5. Betsy Ross Bridge

6. Petty Island

7. Penns Landing/Wiggins Park
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.1Z 11

9. Mouth of Schuylkill 8. Horseshoe Shoal

10. Eddystone
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non-point sources of pollution. Fishing and other recreational activities are
increasing along this reach and the establishment of a viable, although
marginal, year-round fish population has been documented in the study reach as
a result of recent water quality improvements, Important migratory fish
migrate to or through this reach including such important species as the
American shad and striped bass, both the subject of the fisheries management
efforts of the Delaware Basin Fish and Wildlife Cooperative. Short-nose
sturgeon, an endangered fish species, is found in Zone 2 and elsewhere.

In recent years, new fishing access areas and other recreational facilities
have been provided on both sides of the river in Zones 2, 3 and 4 by state
fisheries agencies, coastal zone management programs and by local and state
recreation programs. This trend is expected to continue. In addition, tiger
muskellunge have been stocked by the Pennsylvania Fish Commission since 1984
for sport fishing. In more recent years, an ad-hoc, non-commercial blue crab
f ishery has arisen in Zone 4 as well. Trends indicate that recreational use
of the estuary will likely increase dramatically in the future. The
recreational potential of the Delaware Estuary is immense considering the
number of people residing near by,

Study Approach
The study approach involved a five part process: selection of target fish,
selection of sampling sites, fish collection, fish health analyses, and fish
tissue toxics analyses. The process was a sequential process with the
exception that fish tissue toxics dat a were also reviewed by NJDEP personnel
before the completion of the fish health report. The entire study was
conducted in accordance with a DRBC-prepared Quality Assurance Project Plan
which was approved by the U.S. Environmental Protection Agency.

Selection of Target Fish
Target fish for this study were selected on the basis of their presence and
importance as resident estuary fish, and their importance as a recreational
sport fish (i.e., the likelihood of being both caught and eaten). Ictalurids
(channel catfish, white catfish and brown bullheads) and white perch were
selected with channel catfish being the preferred Ictalurid wherever possible.

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Catfish were considered good target fish for numerous reasons. Various
studies have found the three catfish species throughout the Delaware Estuary.
Fish population data from.the Pennsylvania Fish Commission's 1984-86 surveys
suggested that channel catfish might be more common than brown bullheads and
white catfish but this generality is not applicable to any given site or

season,

Catfish are indiscriminate feeders and eat any form of food from algae to
small fish. Generally considered predominately a bottom feeder, catfish are
opportunists that feed throughout the water column. There is also some belief
that catfish are not wide-ranging, preferring to remain in a local area of the
waterbody although with some seasonal movement. Catfish, by feeding at
different levels in the food chain and throughout the water column and near
bottom sediments, may thus be expected to reflect environmental contaminants
in the estuary, where present. Summertime observations of emaciation suggest
that adult channel catfish in the Delaware Estuary are less healthy than
catfish found elsewhere. In the Delaware Estuary from the Schuylkill River
downstream to Tinicum Island a fish advisory has been issued by Pennsylvania

for channel catfish due to chlordane and PCB exceedence of FDA action levels.

White perch were selected as a target fish because of their abundance in the
estuary and the possibility that they are the most commonly caught and eaten
fish by fishermen. Pennsylvania Fish Commission surveys in the summers of
1984-86 found that white perch was the third most abundant fish species next
to the blueback herring and bay anchovy. Compared to these two fish, however,
white perch was more evenly distributed throughout the estuary and the only
one of the three living within the Delaware River system for its entire life
history.

White perch are generally bottom oriented in their feeding. As larvae and
Juvenile fish, white perch are primarily consumers of plankton. Young fish
eat insect larvae and other macroinvertebrates with adult fish feeding
primarily on small forage fish, crabs, eggs of other species, etc. Unlike
catfish, white perch exhibit extensive seasonal movement within the tidal
Delaware system. In the warmer months, spawning and post-spawning fish are
located in the upper estuary and tributaries. However, as cold weather
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approaches, white perch leave this area for the deeper waters of the lower
Delaware Estuary and Delaware Bay. Because of their life history, it was
believed at the start of the study that white perch would reflect
environmental problems much less than catfish would.

Selection of Sampling Locations
Initially ten general sampling locations for the study were selected from the
29 sampling locations used by the DEL USA water and sediment toxics surveys.
In general, the fish collection locations were selected to represent three
toxic survey sites, i*e*, locations where water and sedimentwere collected
right side, left side and center channel. The initial distribution of the
fish collection sites were one in Zone 2; six in Zone 3; and three in Zone 4.

Fish collection locations were shifted during the study to take advantage of
the completion of the DEL USA report, Toxics Review of the Delaware Estuary.
Based on the analyses of DEL USA and other toxics data, the report recommended
priority attention be given to River Mile segments 93-105 and 114-120 due to
the consistently elevated levels of toxicant contamination which were noted.

As a result the final distribution of fish collection locations were three in
Zone 2, four in Zone 3 and three in Zone 4.

Table 1 compares the initial and final fish collection locations and the fish
collection locations are delineated on Figure 1. Part B contains tabulations
and maps delineating precisely the fish collection sites within each general

location.

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Table 1: Comparison of Initial and Final Fish Collection Sites

Zone Initial (planned) Final (sampled)
2 Upper End of Burlington Island
2 Burlington-Bristol Bridge area Burlington Bristol Bridge area
2 Mouth of Neshaminy Creek
3 Tacony-Palmyra Bridge area Tacony-Palmyra Bridge area
3 Betsy Ross Bridge area Betsy Ross Bridge area
3 Petty Island (lower end) Petty Island (midway)
3 Penns Landing area Penns Landing area
3 Between Penns Landing and
Walt Whitman Bridge
3 Below Walt Whitman Bridge

4 Horseshoe Shoals area Horseshoe Shoals area
4 Mouth of Schuylkill River Mouth of Schuylkill River
4 Eddystone, PA area Eddystone, PA area

Fish collection
The study design called for the collection of at least 900 fish at the ten
fish collection locations including at least 150 target fish. A total of 1301
fish (23 fish species) were collected and enumerated by Rutgers University
personnel. Table 2 summarizes the fish collected. The distribution of the
fish by location and species is presented in Table 3, Part B. Due to the

nature of the collection devices all fish were adult. An additional number of

target fish were also collected by U.S. Fish and Wildlife Service and NJDEP
personnel whose collection activities augmented the Rutgers collection.
Non-target fish were not enumerated by these latter fish collection

activities.

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TABLE 2
SUMMARY OF TOTAL FISH CAPTURED (RUTGERS ONLY)

No. of No. of No. of

Location Fish Caught Fish Species Target Fish Caught
1 100 15 72

2 177 18 59

3 82 11 44

4 128 4 125

5 205 9 186

6 29 4 27

7 353 5 344

8 63 6 60

9 54 6 50

10 110 5 29

Total 1301 23 996

Target fish retained for subsequent analyses were Ictalurids (channel catfish,
white catfish and brown bullheads) and white perch. These fish were delivered
by the collector to NJDEP personnel either f resh or live, depending on the
analyses to be performed. After enumeration and identification, non-target
fish were returned to the estuary except for short-nose sturgeon which were
retained as part of the Rutgers short-nose sturgeon research project.

Most fish were collected with 6-foot d eep experimental gill nets with 2, 3, 4
and 5 inch stretch mesh panels. Some target fish were also collected with a 4
to 8 inch stretch mesh panel gill net, and trot-line. Water quality and other
data collected at each sampling site is presented in Table 2 of Part B.

Fish Health Analyses
Target fish delivered to NJDEP personnel were subsequently analyzed by a fish
pathologist and a wildlife toxicologist for:
o general necropsy (all individual target fish),
o screening for specific pathogens (subsample of total),
o histological examination of any abnormal lesions (on all found),
o general parasite examination (subsample of total),
o biochemical testing of tissues for specific enzymatic compounds.

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Table 3 indicates the number of necropsies which were performed on individual
fish per species and location. Part C, the NJDEP fish health data report,
presents the methodologies used in the fish health component of the study,
study findings and other information.

TABLE 3

NECROPSIES PERFORMED BY SAMPLING LOCATION

SITE 1 2 3 4 5 6 7 8 9 10

White Perch 40 26 35 60 60 21 60 55 5 24

Channel Catfish 6 8 4 9 21 4 3 3 1 4

White Catfish 16 8 4 - - - 16 1 4 -

Brown Bullhead 10 6 1 - 27 - 2 1 1 1

Fish Tissue Analyses
Composites of target fish were prepared by NJDEP for subsequent shipment to
the Philadelphia Academy of Natural Sciences. The goal of the study was to
obtain three composites per sampling location as follows: one composite of
catfish livers, one of catfish fillets and one of white perch fillets. Two
composites of white perch were subsequently analyzed as well. The number of
fish per composite ranged from 1 to 6 with the 5 being the target number. A
total of 31 composites of fillets or livers were analyzed. Table 4 indicates
the distribution of the composites by location, tissue and fish species. The
exact distribution of the composites and the number of fish per composite were
determined by the success of capturing target fish at each location.

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TABLE 4

SUMMARY OF FISH COMPOSITES BY SPECIES AND LOCATION

Site Filets Livers

I WP cc cc

2 WP cc CC WC BB

3 WP cc cc

4 WP cc cc

5 WP cc CC BB WP(2)

6 WP cc cc

7 WP WC WC

8 WP

9 WP cc cc

10 WP

WP = White Perch

CC = Channel Catfish

WC = White Catfish

BB = Brown Bullhead

The fish composites were analyzed for various organic and inorganic toxic
compounds. The parameters analyzed were various pesticides of interest (see
Part D), polychlorinated biphenyls (PCBs), cyanide, antimony, arsenic,
beryllium, cadmium, chromium, copper, lead, mercury, nickel , selenium,
thallium, zinc, and various polynuclear aromatic hydrocarbons. Phenols,
originally scheduled for analyses, were dropped from the parameter list when
EPA determined the standard test methodology used for this parameter was no
longer acceptable. Cyanide became an optional parameter, run only when
sufficient fish tissue remained after the other analyses were completed. With
minor exceptions, the parameters selected for the tissue analyses were
parameters analyzed in the DEL USA water column and sediment surveys of May
and June 1986.

SUINARY OF RESULTS

The following describes, in non-scientific terms, the general findings of this
study. More detailed information is presented in Parts C and D.

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Fish Health

1. Bacterial pathogens Two opportunistic bacterial pathogens were detected

which can result in fish mortalities under conditions of environmental

stress* One of these was positively correlated with higher water
temperature. This pathogen caused eye protrusions in white perch from
-site 8 and subclinical kidney infections in white perch, white catfish and

channel catfish.

2. Parasites. Sixteen species of parasites, three of them potential
pathogens were recovered. One pathogen, the eye fluke, may cause visual
problems for catfish. No environmental significance was attached to the

parasites.

3. Liver tumors. Invasive bile duct tumors were found in 18% of the white

perch with the prevalence increasing with fish length. This condition is
not common and has only been reported once in the literature. Although
the tumors were not statistically correlated with environmental contamin-
ants, the livers of tumor-bearing perch had higher metal levels than did
others. A recent study of Chesapeake Bay white perch suggested that
abnormal copper storage in liver tissue might be associated (along with
other possible factors) to the development of tumors. Very high copper
levels were found in DEL USA white perch liver tissue composites and
levels were higher in tumor bearing perch than those without grossly

visible tumors.

4. Lip tumors and liver lesions. These were found in brown bullheads: lip
tumors at site 10 and liver lesions at site 2, 5 and 10. The latter will
likely develop into tumors* Frequency of occurrence in brown bullheads,
while low, was highest at site 10. The condition may be indicative of
toxics although the small sample sizes and prevalence precluded definitive

conclusions.

5. Liver enzyme assays provided evidence of fish exposure to polynuclear
aromatic hydrocarbons (PAHs or PNAs) at sites 7 and 10. The DEL USA toxic
surveys identified PAHs in the sediment at site 7. Exposure of f ish at
site 10 provide a circumstantial link between PAHs and the brown bullhead

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tumors discussed in 4 above. A relationship between tumors and PAHs has
been theorized by others in the literature.

6. Gill pathology. A non-specific lesion or growth due to increased cell
growth was evident in target fish. It was most severe in fish from sites
6 through 10 and particularly site 6. The lesions are possibly due to low
dissolved oxygen conditions or environmental contaminants. It is of note
that the bottom of the estuary dissolved oxygen sag is generally found in

the reach of river between sites 6 and 10.

7. Miscellaneous. Various fish individuals showed emaciation (30% less than
normal weight-length relationship), liver enlargement (channel catfish)
and asciles (fluid buildup).

fish Tissue Toxics
1. Organics Organic pollutants found in fish tissue were PCBs and the

metabolites of DDT: DDE and DDD. PAHs were not found. PCBs found were,
Aroclors 1254 and 1260. Aroclors refer to types of PCSs that were
produced commercially. For example Aroclor 1254 contains 12% carbon and

54% chlorine.

PCBs and the DDT metabolites were highest in channel catfish samples
(fillet and liver) with six of the seven fillet composites exceeding the
FDA Action Level. Two of these samples were 2 to 2.5 times greater than
the FDA limit. One white perch liver sample was high in PCBs and, in
fact, had the highest PCB value observed. The corresponding fillet
sample, however, while higher in PCBs than brown bullhead, white catfish
and other white perch composites, did not exceed the FDA Action limit.
Chlordane was found in all samples having PCBs but it was not quantified.
Based on past Delaware Estuary studies, it can be assumed that chlordane
was present at problem levels.

2. Metals. All but three of the 12 metals examined were found in most fish

composites. Arsenic was found only in channel catfish and white perch.
These two species had similar metal levels in the fillet samples (except
for selenium). White perch, however, had higher liver metal levels than

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channel catfish for arsenic, cadmium, nickel and particularly copper; zinc
and selenium. The data indicate that fish species accumulate toxics
differently and that this distinction includes members within a family
(e.g., the catfish species).

Overall Summary
The many fish examined during this study were reasonably healthy although
affected by physical stresses such as seasonal high water temperature, low
dissolved oxygen, the onset of spawning and other environmental factors. A
range of fish health problems were observed. This range, however, is
analogous to the range of health problems that might be anticipated if a
random sample of 996 individuals from any wild fish population were analyzed.
Circumstantial evidence indicate that toxics may be affecting fish health in
some cases. No conclusive evidence exists, however, that toxics are currently
limiting fish populations or would prevent increases in fish populations if,
for example, dissolved oxygen levels in the estuary were raised.

As would be expected, fish in the Delaware Estuary have accumulated various
heavy metals, organics and other contaminants in their tissue. Table 5
compares heavy metal concentrations from several studies with the DEL USA
ranges. The contaminants in fish tissue are generally the same as are found
in estuary sediments and water. The data indicate that eating some fish
caught in the estuary is probably unhealthy and that the consumption of
channel catfish should be avoided.. PCBs indicated as a problem parameter in
past fish testing, is indicative of an extremely persistent problem. A
problem with chlordane, unquantified by the study, is indicated as well.

Table 6 tabulates (to the degree possible) the major study findings by
sampling site. The tabulation is presented in order to determine whether or
not the study findings are evenly distributed or, rather, whether fish from
some sites have more "problems" than others. The items listed are not
necessarily equally important nor related to each other. A tabulation of the
number of times a site appeared in Table 6 is shown in Table 7. As would be
expected, the number of citations is greater for Zone 3 and 4 locations than

Zone 2 locations.

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Table 5
Comparison of Heavy Metals in DEL USA Fish
With Several Past Sampling Efforts

1977 1981 1978-80 1978 DEL USA DEL USA
PADER PADER NYDEC Tennessee Channel Catfish White Perch

Cd N.D - 0.24 0.050 - 5.34 <0.01 - 0.05 0 - 1.70 <0.020 - 0.064 0.027 - 0.104
Cr N.D - 13.93 0.400 - 1.42 0.03 - 0.14 0 - 0.35 1.120 - 6.920 0.970 - 3.020
Cu 0.09 - 9.76 0.670 - 14.97 0.48 - 0.88 0 - 10.50 2.310 - 7.660 2.260 - 10.600

Pb N.D - 15.86 <0.005 - 12.43 - 0 - 0.90 0.137 - 1.110 0.187 - 0.385
Nl N.D - 7.53 - - - 0.730 - 2.070 1.150 - 3.130
Zn 4.47 -'30.50 - 5.30 - 12.40 - 21.400 - 28.200 23.600 - 30.900

As N.D - 0.30 - <0.10 - 2.90 - <0.600 - 1.120 <0.600 - 2.200

Se N.D - 3.34 - - - 0.832 - 1.100 3.030 - 4.560

N *D None detected

Non DEL USA values for edible portion of fish as reported in Concentrations of Environmental Contaminants in
Fish from Selected Waters in Pennsylvania- (U.S. Fish and Wildlife Service, 1984). Ranges for PADER
include data from Delaware Estuary fish. See Part D, Table 3 for a comparison of heavy metals found in
fish tissue in specific U.S. rivers and fish species.

Table 6
Summary of various study study findings by site

CC = channel catfish BB = brown bullhead
WP = white perch WC = white catfish

Condition Site
CC emaciation 6
WP emaciation 8
CC enlarged livers 5/6
BB lip tumors 10
Grade 2/3 Gill hyperplasia - WC 6
Grade 2/3 Gill hyperplasia - WP 6
Grade 2/3 Gill hyperplasia - BB 7 thru 10
high frequency Aeromonas hydrophila 5
highest frequency WP liver tumors 9
significantly higher CC hepatic AHH Activity 10
significantly higher WC hepatic AHR Activity 7
WP - grossly visible liver tumors 5, 10
.highest Cd- CC muscle 5
highest Cd - WP muscle 5
highest Cr - CC muscle 10
highest Cr - WP muscle 3
highest Pb - CC muscle 9
highest Pb - WP muscle 9
highest Ni - CC muscle 5
highest Ni - WP muscle 9
highest Zn - CC muscle 4
highest Zn - WP muscle 7
highest As - CC muscle 1
highest As - WP muscle 9
highest Se - CC muscle 9
highest Cd - CC liver 2
highest Cr - CC liver 9
highest Cu - CC liver 2
highest Pb - CC liver 3
highest Ni - CC liver 3
highest Zn - CC liver 9
highest As - CC liver 2
highest Se - CC liver 1
highest CC PCBs muscle 5
highest WP PCBs muscle 7
highest CC DDE muscle 5
highest WP DDE muscle 7
highest CC DDD muscle 5
highest WP DDD muscle 7
highest CC PCBs liver 9
highest CC DDE liver 5
highest CC DDD liver 5

Table 7
summary of Table 6 citations by site

Site Zone Number, of times cited in Table 6

2 2

2 2 4

3 2 3

.4 3 1

5 3 10

6 3 4

7 3 4*

8 3/4 2*

9 4 10
10 4 6*@

No ch annel catfish tissue examined at these sites

-17-

An issue germane to the DEL USA project is the relationship of fish edibility
concerns (i.e., human health concerns) to the federal fishable water quality
goal which only addresses fish health concerns. Is the fishable water quality
goal "attainable" if some fish cannot be eaten after a viable fishery is
restored? The results of this study certainly indicate the need for increased
toxics management and control programs plus more extensive fish tissue
monitoring - fish consumption advisory networks in the estuary* However,
edibility problems should not be used to justify water quality that does not
adequately protect aquatic life. Higher dissolved oxygen standards, for
example, benefit the entire estuary ecosystem including 30 to 40 species of
fish. These benefits should not be subordinate to edibility concerns in a few
fish species.

This study, like other DEL USA toxics studies, was designed to be a
reconnaissance study - a first look at possible fish health, fish tissue
toxics and estuary contamination relationships. The study findings indicate
that these relationships do exist. Future estuary studies, including those
recommended below, will build on this data base. Some of this new information
may lead to more definitive interpretations of the data and findings of this
study.

The data presented herein add to the body of knowledge about fish tissue
contamination in the estuary. Unfortunately, this body of knowledge resides
in various forms with many state and federal agencies that collect this type
of information. Due to the lack of resources, the compilation and analysis of
these past fish tissue data was not possible and, thus, not included as part
of this report. Based on the findings of this report a comprehensive evalua-
tion of the available fish tissue data appears warranted.

Recommendations

1. The most immediate concern raised by this study is the apparent high PCB
(and possibly chlordane) levels found in channel catfish. Based on the
widespread locations where PCB concentrations were found, an estuary-wide
fish advisory for channel catfish should be considered in order to protect

human health.

2. Regardless whether or not an advisory is issued as in I above, a
systematic approach for monitoring fish contamination is needed. This
need will increase as the fishing potential of the estuary is discovered
by the fishing public. The systematic approach should consist of the
following steps:

ae the collection, compilation and evaluation of all available fish
tissue toxics data for historical trends, spatial extent of toxics,
levels of parameters of concern, species, and so forth, plus an
evaluation of existing fish tissue monitoring programs for their
extent of coverage, frequency, strengths and weaknesses,

b. the conduct of creel surveys to assess fishing activity, species
caught and species kept for consumption,

ce the development of a coordinated, unified multi-agency fish tissue
monitoring plan covering all estuary zones with delegated responsi-
bilities, uniform reporting procedures, and, if applicable, joint fish
advisory procedures,

d. implementation of c. above on a trial basis with adjustments made

thereafter.

Logically, development of the systematic approach should be extended to
include both- the non-tidal Delaware River and Delaware Bay. The inter-
state nature of the problem indicates plan development (primary responsi-
bility) should be delegated to the Delaware River Basin Commission, the
Delaware Bay Fish and Wildlife Cooperative, the U.S. Fish and Wildlife
Service, or a special committee established specifically for the task.
Agencies implementing the program would be delegated by the plan.

3. The concern for toxic contamination should extend throughout the estuary
food chain from first level carnivores through waterfowl and other
wildlif e. In other words, while fish and human health considerations are
primary concerns, ecosystem considerations should not be ignored.

_19-

4. Fish contamination is only one part of an overall toxics problem. Efforts
to initiate an interstate toxics control strategy for the estuary and
basic research into the fate and transport of toxics in the estuary (such
as the ongoing Academy of Natural Sciences study) should be accelerate d.

5. Two fish health conditions observed during this study warrant followup
studies. These are (1) the liver tumors in white perch which may be
related to environmental contaminants, and (2) the tumors in brown
bullheads that might be associated with PAHs. Specific recommendations
concerning these followup studies are presented in Part C.

6. Additional fish pathology and toxicology (i.e., fish health) studies
should be conducted in the estuary by the fish management agencies. Such
studies should address additional fish species and seasons preferably as
part of a year-round or multi-year study.

7. The inter-relationships between fish health, water temperature and
dissolved oxygen concentrations suggest the need to address, on a
comprehensive basis, the possible cumulative impact of heated discharges
on estuary ambient water temperatures and the possible additional
environmental stress imposed on aquatic life (as indicated herein).
Logically, such studies should include impingement/ ent rainment issues as

well.

-20-

I
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PART B - DATA FROM FISH COLLECTION ACTIVITIES
I RUT.GERS, THE STATE UNIVERSITY
I
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Table 1. Sampling locations and fishes collected for the DRBC Delaware
Estuary Fish Health and Contamination Study, October, 1986
July, 1987.

I.' Upper end - Burlington Island. Sampled July 9, 1987.
A. 20 m below Buoy.52 and 10 m into"[email protected] from the New Jersey side.
Cyprinus carpio (1) [SN-11981*
B. 20 m below Buoy 53 and 10 m into the channel from the Pennsylvania side.
No fish taken. [SN-1199]
C. New Jersey shallows abreast Buoy 52.
Brevoortia tVrannus (2) [SN-12001
Dorosoma cepedianum (2) Ictalurus nebulosus-(4)
Cyprinus-carpio (1) Ictalurus punctatu .(l)
Notemigonu crysoleucas (1) Morone americana (23)
Catostomus commersoni (3) Lepomi pibbosu (1)
Ictalurus catus (4) Perca f lavescens (1)
D. New Jetsey shallows 150 m below Buoy 52.
Alosa pseudoharenpus (1) [SN-12011
Brevoortia tyrannus (1) Ictalurus punctatus (5)
Dorosoma cepedianum (4) Morone americana (17)
Notropis hudsonius (1) Morone saxatilis (1)
Catostomus commersoni (6) Lepomi gibbosus (1)
Ictalurus catus (12) Stizost ediomvitreum vitreum (1)
Ictalurus nebulosus (6)

2. Burlington-Bristol Bridge area. Sampled October 28, 1986.
A. Mid-channel abreast rangefinder dolphin across from Burlington Generating
Station.
No-fish taken. [SN-10901
B. 40 m above rangefinder dolphin across from Burlington Generating Station.
Morone americana (2) [SN-10911
C. Mid-channel immediately below Burlington-Bristol Bridge.
Acipenser brevirostrum (3) (SN-1093]
Ictalurus catus (2)
Ictalurus punctataus (2)
Morone americana (5)

Burlington-Bristol Bridge area. Sampled July 6, 1987.
A. Directly between Burlington-Bristol Bridge and upstream end of bulkhead
at Burlington-Generating Station, along channel edge from New Jersey side.
Acipenser brevirostrum (2) [SN-11941
Ictalurus punctatus 72)
B. Abreast rangefinder dolphin across::from.Burlington Generating Station,
along channel edge from Pennsylvania side.
Ictalurus punctatu .(2) [SN-11951
C. Pennsylvania shallows abreast rangefinder dolphin across from Burlington
Generating Station.
Anguilla rostrata (1) [SN-11961
Brevoortia tyrannus (44) Ictalurus nebulosus (1)
Dorosoma cepedianum (1) Morone americana (10)
Notemigonus crysoleucas (7) Lepomis gibbosus (3)
Ta-tostomus c-ommersoni Micropterus salmoides (1)
Ictalurus catus (1)

(Table I continued)
(2. Burlington-Bristol Bridge area. Sampled July 6, 1987 continued)

D. Pennsylvania shallows immediately abreast Burlington Generating Station.
Alosa Dseud oharenws (4) [SN-11971
Brei . 'annus (32) Ictalurus nebulosus (5)
Dorosoma cepedianum (6) Ictalurus punctatus (4)
Esox lucius, X E. masquinongy (1) Morone americana (16)
Cyprinus carplo (2) Morone saxatilis (4)
Notemigonus crysoleucaf (3) Ambloplites rupestris (1)
Catostomus commersoni (1) Pomoxis nigromaculatus (1)
Ictalurus catus (4)

3. At or above the Mouth of Neshaminy Creek. Sampled June 29, 1987.
A. 100 m below Buoy 36, along channel edge from New Jersey side.
No fish taken. [SN-11901
B. Pennsylvania shallows 100 m below riverfront boat ramp at Neshaminy Creek
Marina.
Brevoortia tyrannus (13) [SN-11911
Dorosoma cepedianum (5) Ictalurus nebulosus (1)
Cyprinu carpio (1) Morone americana*(13)
Notemigonus crysoleucaa (2) Micropterus.salmoides (1)
C. New Jersey shallows 100 m above Buoy 36.
Alosa pseudoharengus (2) [SN-11921
Brevoortia tyrannus (6) Ictalurus punctatu (4)
Dorosoma cepedianum ' (3) Morone americana (22)
Cyprinus carpio (1) Lepomis Ribbosus (2)
Ictalurus catus (4)
D. 100 m below riverfront boat ramp at Neshaminy Creek Marina along channel
edge from Pennsylvania side.
Cyprinus carpio (2) [SN-11931

4. Tacony-Palmy ra Bridge area: Sampled June 11, 1987^
A. 100 m below Buoy 8 and 10 m into the channel from the New Jersey side.
No fish taken. [SN-11821
B. 100 m below Buoy 10 along channel edge from New Jersey side.
No fish taken. [SN-11831
C. New Jersey shallows 100 m below Buoy 8.
Dorosoma cepedianum (1) [SN-1184]
Ictalurus punctatus (4)
Morone americana (3)
Morone saxatilis (1)
D. Pennsylvania shallows immediately above Buoy 6.
Ictalurus punctatus (5) [SN-11851
Morone americana (113)
Morone saxatilis (1)

5. Betsy Ross Bridge area. Sampled June 18, 1987.
A. 150 m below Conrail Bridge along channel edge from Pennsylvania side.
No fish taken. (SN-11861
B. 100 m below Buoy 2 along channel edge from New Jersey side.
Ictalurus punctatus (3) [SN-11871
Morone americana (1)

(Table 1 continued)
(5. Betsy Ross Bridge area. Sampled June 18, 1987 continued)

C. Pennsylvania shallows between Betsy Ross Bridge and Frankford Creek.
Dorosoma.cepedianum (1) [SN-11881
Cyprinus carpio (5) Morone americana (82)
Ictalurus nebulosus (27) Morone saxatilis (2)
Ictalurus punctatus (14)
D. New Jersey shallows immediately below Betsy Ross Bridge.
Carassius auratus (5) [SN-1189]
Cyprinus carpio (2) Morone americana (55)
Catostomus commersoni (1) Lepomis Ribbosus (3)
Ictalurus punctatus (3)

6. Midway along Petty Island. Sampled May 28, 1987.
A. 200 m above Pier 11, Port Richmond, along channel edge from Pennsylvania
side.
No fish taken. (SN-11731
B. 200 m below Mooring Buoy A along channel edge from New Jersey side.
Acipenser brevirostrum (1) [SN-11741
Ictalurus punctatus (1)
C. New Jersey shallows abreast Mooring Buoy A.
Ictalurus punctatus (3) [SN-1175]
Morone americana, (4)
D. New Jersey shallows immediately below Mooring Buoy B.
Morone americana (6) [SN-11761
E. Pennsylvania shallows 200 m above Pier 11, Port Richmond, within
interpier area. .
Alosa pseud6harengus (1) [SN-1177]
Morone americana (13)

7. Penns Landing/Wiggins Park area. Sampled May 18,1987.
A. Abreast Wiggins Park close to, but not inside, Anchorage-Area 13 from the
New Jersey side.
No fish taken. [SN-1168]
B. Abreast restaurant ship 'Moshulu' along upstream half of Penns Landing
along channel edge from Pennsylvania side.
No fish taken. [SN-1169]
C. 50 m below Benjamin Franklin Bridge in line with pier faces along New
Jersey side.
Morone americana (7) [SN-1170]
D. 30 m below face of pier to RCA, Camden
Alosa aestivalis (6) [SN-11711
Ictalurus catus (14)
Ictalurus punctatus (3)
Morone americana (262)
E. New Jersey shallows 50 m below Benjamin Franklin Bridge within interpier
area*
Alosa aestivalis (3) [SN-11721
Ictalurus catu .(2)
Ictalurus nebulosus (2)
Morone americana (54)

(Table 1 continued)

8. Horseshoe Shoals area. Sampled May 11, 1987.
A. 40 m below Buoy 37 along channel edge from Pennsylvania side.
No fish taken. [SN-1164]
B. 100 m above Buoy 46A along channel edge from New Jersey side.
No fish taken. [SN-11651
C. Immediately below Buoy 37 and 100 m out of the channel from the
Pennsylvania side.
Alosa aestivalis (1) [SN-11661
Ictalurus catus (1)
Ictalurus punctatus (1)
Morone americana (15)
D.' Pennsylvania shallows immediately below Buoy 37'.
Acipenser brevirostrum (1) [SN-11671
Alosa aestivalis (1) Morone americana (40)
Ictalurus nebulosus (1)
Ictalurus punctatus (2)

9. Mouth of Schuylkill River. Sampled May.1,1987.
A. Immediately above Buoy 44 along channel edge from New Jersey side.
No fish taken. [SN-1152]
B. Immediately below Buoy I along channel edge from Pennsylvania side.
Ictalurus catus (2) [SN-11531
C. Abreast Buoy I and 30 m out of the Schuylkill River mouth channel from
the Mud Island, Pennsylvania side.
Alosa aestivalis (1) (SN-1154]
Dorosoma cepedianum (2)
Ictalurus catus (3)
Ictalurus nebulosus (1)
D. Immediately above Buoy 44 and 50 m out of the channel from the New Jersey
side.
Alosa aestivalis (1) [SN-11551
Ictalurus vunctatus (1)
Morone americana (43)

10. Eddystone. Sampled June 4, 1987.
A. 100 m above Buoy 4T and 10 m out of the channel from the New Jersey side.
Ictalurus punctatus (1) [SN-1178]
B. New Jersey shallows immediately below Buoy 2T.
Alosa aestivalis (1) [SN-1179]
Brevoortia tyrannnus (49)
Ictalurus punctatus (3)
Morone americana.(15)
C. Pennsylvania shallows 250 m below downstream end of Little Tinicum Island.
Brevoortia tyrannus (31) (SN-1180]
Ictalurus nebulosus (1)
Morone americana (9)
D. 150 m below Buot 3T and 20 m into the channel from the Pennsylvania side.
No fish taken. [SN-1181]

This is a Shortnose Sturgeon Project collection number.

W-W low go

Table 2. Water quality data taken at sites of fish sampling for the DRBC Delaware Estuary Fish Health and Contamination Study,
October, 1986 - July, 1987.

Cur-rent
Tim Depth Temperature T Dissolved 0 Secchi Velocity Direction
Locale Coll. Date (EST) (m) Bott. Surf. Bott. Surf . (m) Tide (nvs)

1 SN-1198 07/09/87 1027 15.5 26.2 26.3 3.94 4.30 0.55 flood 42.8 upstream
SN-1199 07/09/87 1044 11.3 26.2 26.5 3.99 4.70 0.80 flood 11.7 upstream
SN-1200 07/09/87 1001 2.4 26.7 26.7 5.06 5.01 0.75 flood 40.4 downstream
3@4201 07/09/87 0929 2.4 26.5 26.6 5.29 5.72 0.70 flood 24.3 downstream

2. SN-1090 10/28/86 0935 11.9 13.2 13.4 8.68 8.81 1.60 flood 19.6 upstream
Sn--1091 10/28/86 (See SN-1090)
SN-1093 10/28/86 1230 18.0 13.3 13.4 8.62 8.74 1.55 ebb 70.9 downstream
SN-1194 07/06/87 0931 14.3 25.2 25.5 4.58 5.20 0.45 flood 5.4 upstream
SN-1195 07/06/87 0912 13.1 25.3 25.4 4.54 5.10 0.50 flood 19.6 upstream
SN-11% 07/06/87 0855 2.4 25.1 25.2 4.90 5.23 0.45 flood + downstream
07/06/87 0837 2.4 25.2 25.3 4.76 5.08 0.50 flood + downstream
Un
3. SN-1190 06/29/87 1040 8.2 25.1 25.2 4.90 6.19 1.20 ebb 32.1 downstream
SN-1191 06/29/87 1023 1.2 25.7 25.6 6.21 6.19 0.60 ebb + upstream
St@-1192 06/29/87 1103 2.4 25.1 25.7 5.70 6.45 1.00 ebb + downstream
SN-1193 06/29/87 0939 9.8 25.1 25.2 5.25 5.49 1.15 ebb 37.2 downstream

4. SN-1182 06/11/87 1007 14.6 22.8 22.9 4.20 4.45 1.60 flood 109.0 upstream
W-1183 06/11/87 0938 13.8 22.8 22.8 4.70 4.83 2.00 flood 67.5 upstream
SN-1184 06/29/87 0921 3.0 22.4 22.4 4.99 5.03 1.40 flood 66.7 upstream
SN-1185 06/29/87 0903 2.7 22.8 22.9 4.00 4.26 1.50 flood 28.0 upstream

5. SN-1186 06/18/87 0944 12.2 23.8 23.8 3.98 4.00 1.50 ebb 60.4 downstream
34-1187 06/18/87 1022 12.2 23.9 24.0 5.22 5.34 1.65 ebb 83.4 downstream
S\L-1 188 06/18/87 1048 1.2 24.1 24.2 3.95 4.00 1.40 ebb 38.3 downstream
SN-1189 06/18/87 1145 1.2 24.5 24.5 7.34 7.34 0.80 ebb 0.0 none

6. 9@4173 05/28/87 0811 10.7 18.6 18.7 4.81 5.17 2.00 ebb 32.6 downstream
SN-1174 05/28/87 1055 13.8 18.6 18.6 5.20 5.30 1.60 flood 91.0 upstream
SNI-1175 05/28/87 1032 5.5 18.6 18.7 5.60 5.67 1.35 flood 62.3 upstream
SN-1176 05/28/87 1009 3.4 18.5 18.6 5.43 5.61 1.50 flood 31.8 upstream
SNL-1177 05/28/87 1515 3.0 (See SN-1173)

(Table 2 continued)

Current
Time Depth Temperature OC Dissolved 0, (m) Secchi Velocity Direction
Locale Coll. Date (EST) W Bott. Surf . Bott. Surf. W Tide ON

7. SN-1168 05/18/87 0807 11.3 17.1 17.2 8.30 8.56 1.20 ebb 46.3 downstream
S[+-1169 05/18/87 1023 12.2 17.2 17.2 7.99 8.10 1.25 ebb 58.7 downstream
SN-1170 05/18/87 1003 '7.6 17.3 17.5 8.78 9.72 1.20 ebb 59.6 downstream
SN-1171 05/18/87 0935 12.5 17.2 17.3 8.58 9.18 1.10 ebb 0.0 none
3@4172 05/18/87 (See SN-1170)

8. SN-1164 05/11/87 1004 13.7 15.0 15.0 7.38 7.50 1.10 flood 75.2 upstream
SN-1165 05/11/87 1037 14.9 15.0 15.3 7.18 7.50 1.60 flood 33.6 upstream
SN-1166 05/11/87 0939 6.7 15.0 15.0 7.01 7.12 0.95 flood 70.1 upstream
SN-1167 05/11/87 0912 7.3 15.0 15.0 6.90 7.01 1.10 flood 68.9 upstream

9. SN-1152 05/01/87 0804 15.5 13.3 13.3 7.92 8.09 1.30 ebb 90.4 downstream
SN-1153 05/01/87 0845 9.8 13.7 13.5 7.18 7.68 1.30 ebb 44.6 downstream
34-1154 05/01/87 0927 5.8 13.7 13.4 7.19 7.62 1.40 ebb 34.9 downstream
EN-1155 05/01/87 1005 12.2 13.3 13.3 7.82 7.98 1.40 ebb 67.1 downstream

10. SN-1178 06/04/87 1110 10.4 21.7 21.7 3.18 3.27 1.40 ebb 79.4 downstream
SN-1179 06/04/87 1028 2.1 21.7 21.4 3.60 3.76 1.15 ebb 58.3 downstream
SN-118D 06/C4/87 1009 3.4 21.2 21.5 3.85 3.78 1.10 ebb 24.9 downstream
SN-1181 06/C4/87 0938 14.3 21.6 21.7 3.20 3.32 1.15 ebb 87.4 downstream

1. - Upper end - Burlington Island. 6. - Midway along Petty Island.
2. - Burlington-Bristol Bridge area. 7. - Pam Landing/Wiggins Park area.
3. - At or above the Mouth of Neshaminy Creek. 8. - Horseshoe Shoals area.
4. - Tacony-Falmyra Bridge area. 9. - Mouth of Schuylkill River.
5. - Betsy Ross Bridge area. 10. - Eddystone.

These are Shortnose Sturgeon Project collection numbers.

Table 3. Total species list and abundance of fishes captured for the DRBC Delaware Estuary Fish Health and Contardnation Study,
October, 1986 - July, 1%7.

Species Nmbers captured at each samling, localq*
LOCALE: 1 2 3 4 5 6 7 8 9 Total

Shortnose sturgeon 0 5 0 0 0 1 0 1 0 0 7
Acipenser brevirostrLm

Affm-ican eel 0 1 0 0 0 0 0 0 0 0 1
Anguilla rostrata

Blueback herring 0 0 0 0 0 0 9 2 2 1 14
Alosa aestivalis

Alewife 1 4 2 0 0 1 0 0 0 0 8
Alosa pseudobarengus

Menhaden 3 76 19 0 0 0 0 0 0 80 178
Brevoortia tyr-amus

Gizzard shad 6 7 8 1 1 0 0 0 2 0 .25
Doroscm- cepedianun

Tiger muskellunge 0 1 0 0 0 0 0 0 0 0 1
Esox lucius X E. nasquinongy

Goldfish 0 0 0 0 5 0 0 0 0 0 5
Carassius auratus

Cmmn carp 2 2 4 0 7 0 0 0 0 0 15
Cyprinus.carplo

Golden shiner 1 10 2 0 0 0 0 0 0 0 13
Notemimonus crysoleucas

Spottai-1 shiner 1 0 0 0 0 0 0 0 0 0 1
Notropis hudsonius

White sucker 9 2 0 0 1 0 0 0 0 0 12
Catostamis ccnuersoni

(Table 3 continued)

Species Numbers captured at each sampling locale
1 2 3 4 5 6 7 8 9 10 Total

White catfish 16 10** 4 0 0 0 16 1 '5 0 52
Ictalurus catus

Brown bullhead 10 6 1 0 27 0 2 1 1 1 49
Ictalurus nebulosus

Channel catfish 6 10 4 9 2P-11* 4 3 3 1 4 65
Ictalurus; punctatus

White perch 40 33 35 116 138 23 323 55 43 24 830
@brone americana

Striped bass 1 4 0 2 2 0 0 0 0 0 9
%rone saxatilis

Rock bass 0 1 0 0 0 0 0 0 0 0 1
Ambloplites rupestris

Rvpkinseed 2 3 2 0 3 0 0 0 0 0 10
LePcnAs gibbosus

Largeriouffi hiss 0 1 1 0 0 0 0 0 0 0 2
Micropterus salmoides

Black crappie 0 1 0 0 0 0 0 0 0 0 1
Pcmoxis nigranaculatus

Yellow perdi 1 0 0 0 0 0 0 0 0 0 1
Perca flavescens

Walleye 1 0 0 0 0 0 0 0 0 0 1
Stizostedion vitreum vitrem
Total: 100 177 82 128 205 29 353 63 54 110 1301

Imi Mo. no Wm a" Zoo wff-@ wa so

ma "0

(Table 3 continued)

1. - Upper end - BurLington Island. 6. - Yddway along Petty Island.
2. - Burlington7-Bristol Bridge area. 7. - Penns landing/Wiggins Park area.
3. - At or above the Mouth of NeshaTdny Creek. 8. - Horseshoe Shoals area.
4. - Tacony40myra Bridge area. 9. - Mouth of Schuylkill River.
5. - Betsy Ross Bridge area. 10. - Eddystone.

T[wee Wcen by angling.

One taken by angling.

PART C - FISH HEALTH DATA REPORT

NEW JERSEY DEPARTMENT OF ENVIRONMENTAL PROTECTION

INTRODUCTION

This study was conducted to provide data on fish health
in the Delaware River Estuary, to investigate potential
relationships between fish health and toxic substances in the
environment, and to provide an assessment of the general
health of fish from various locations in the estuary. The
study was designed using a variety of examinations and
diagnostic procedures to obtain the data necessary to
accomplish those objectives. Adult catfish and white perch
were selected as target species.
Catfish were chosen for the study because 1) they are
bottom-dwelling species that live and feed in close proximity
to sediments which are a potential source of contaminants,
2) although reported to make random or seasonal movements
(Calhoun 1966), they were considered more location-specific
than other species of fish common in the Delaware Estuary,
and 3) channel catfish were thought to comprise a significant
portion of the sport fish catch in the study area and
O-erefore would be important from an edible standards
perspective. White perch were added as target species
because they are relatively abundant in the estuary and,
because they also comprise a significant portion of the sport
catch in the study area.
Procedures comprising the study were necropsy,
bacteriological screening, parasitological examination,
histological examination, liver enzyme assay, and tissue
analysis. All procedures except the tissue analysis were
performed by personnel of the New Jersey Division of Fish,
Game, and Wildlife and are the subject of this report.
Necropsies were conducted to detect any gross changes in
tissues that might be significant to the health of the fish.
Coincidentally, information necessary for the calculation of
organosomatic indices and condition factors was obtained.
Condition factor or coefficient of condition is a measure of
the relative robustness of the fish (Lagler 1971). Liver
somatic index is a more sensitive measure of the nutritional
status of fish (Heidinger and Crawford 1977). Other studies
have used similar measures of relative liver weight in
studies on the., effects of water pollution and on tumor
incidence in fish (Slooff et al. 1983; Fabacher and Baumann
1985). In this study, the condition factor and liver somatic
index are used to measure differences in condition of fish
between s-ampling locations, and differences in condition of
fish with and without various pathological conditions.
Aeromonas hydrophila and Flexibacter columnaris are
ubiquitous bacteria which may cause disease in fish which
have been stressed (Post 1983). Aeromonas hydrophila is
common in the gut flora of healthy fish in fresh waters
(Trust et al. 1974; MacFarlane et al. 1986 b). When fish are

C-1

stressed, some strains of A. hydrophila may become pathogenic
and cause systemic infections of motile aeromonad septicemia
(Cipriano et al. 1984). The disease has been reported in
catfish following episodes of sublethal hypoxia (Rock and
Nelson 1965; Plumb et al. 1976), and in suckers after
exposure to high levels of copper and zinc (Pippy and Hare
1969). Outbreaks often occur in the spring (Snieszko 1983);
and are probably induced by stress associated with increasing
water temperature and spawning of warmwater fish. Disease
due to Flexibacter columnaris is also related to stress.
Susceptibility of fish is influenced by water temperature
(Becker and Fujihara 1978) and exposure to metals (MacFarlane
et al. 1986a). The prevalence of these organisms among the
gill and gut flora of fish was determined to evaluate the
potential for epizootics if fish were subjected to
environmental stress. Gross sings of disease, culture from
kidneys, and histopathologic examinations were used to
detect clinical infections.
Parasites are often overlooked in fish health surveys
because they usually occur in a symbiotic relationship with
fish and have little effect on their hosts. However, there
is evidence that some parasites are pathogenic among wild
fish populations and may cause direct mortality or make fish
more susceptible to environmental stressors (Sindermann
1986). A parasite survey was included in the present study
to assess the contribution of parasites to the pathology
observed, and to determine whether any parasites were present
that might adversely affect the aesthetic appearance of the
fish to anglers.
Histological examinations were performed on gills and
livers of fish in this study. Gills are the interface
between the fish's circulatory system and the outside
environment. Due to their intimate contact with the water
they display pathologic changes caused by environmental
irritants. The liver functions as a detoxifying organ, and
as such may display the effects of toxins produced by
pathogenic organisms or from exposure to toxins in the
environment.
A number of fish species have been shown to possess a
group of enzymes known as mixed function oxidases (MFOs) that
are involved in the metabolism of various lipophilic organic
compounds (see Chambers and Yarbrough, 1976). Increased
activity of one type of MFO, aryl hydrocarbon hydroxylase
(AHH), is induced when fish are exposed to petroleum
contamination (Payne and Penrose, 1975). Measurements of AHH
activity have been used successfully in field studies to
indicate the exposure of fish to elevated levels of petroleum
compounds (Stegeman, 1978; Davies and Bell, 1984; Luxon et
al. 1987). In addition to being useful indicators of
exposure, MFOs are also important toxicologically because of
their role in the oxidation of polycyclic aromatic

C-2

hydrocarbons (PAHs). These reactions act primarily to
increase the water solubility of the compounds, thus
enhancing the ability of the organism to excrete them.
However, many PA'Hs are converted to carcinogenic
intermediates in this process (Neff, 1979). Exposure to high
concentrations of PAHs is a suspected cause of elevated tumor
frequencies in some fish populations (Baumann et al. 1982;
Baumann et al. 1987). In this study the hepatic AHH
activities of fish from different areas of the Delaware River
are compared in an attempt to identify areas where fish are
exposed to elevated levels of aryl hydrocarbon contaminants.
The data were examined to look for relationships between AHH
activity and tumor incidence in fish from different areas of
the river.
Results of all examinations and assays performed are
presented in this report. The results were evaluated to
compare fish health among locations within the Delaware River
Estuary, and to provide an overall assessment of fish health.

C-3

MATERIALS AND METHODS

The study area consisted of ten sampling sites on the
Delaware River Estuary between river miles 84 and 120. The
sites and their approximate river miles were as follows:

1) Burlington Island (river mile 120)
2) Burlington-Bristol Bridge (river mile 118)
3) mouth of Neshaminy Creek (river 'mile 116)
4) Tacony-Palmyra Bridge (river mile 107)
5) Betsy Ross Bridge (river mile 104)
6) Petty Island (river mile 102)
7) Penns Landing (river mile 99)
8) Horseshoe Shoals (river mile 95)
9) mouth of Schuylkill River (river mile 92)
10) Paulsboro-Eddystone area (river mile 84.5)

Fish were collected from all sites by John O'Herron of
Rutgers University between October 28, 1986 and July 9, 1987.
Sampling was done primarily by gill netting. Details of the
sampling can be found in part B of this report. Additional
samples were collected with gill nets from site 10 by the
U.S. Fish and Wildlife Service on November 8, 1986, and with
set trot lines from site 9 by the N.J. Division of Fish,
Game, and Wildlife on September 25, 1987.
White perch were transported on ice to the Pequest
Hatchery laboratory where pathological examinations were
conducted. When possible, catfish were transported live to
the laboratory, and killed by a blow to the head immediately
prior to necropsy. That method of killing was employed in
place of anesthesia to avoid chemical contamination of
samples used for enzyme assays and tissue analyses.
Necropsies were performed on a maximum of 60 fish of each
species from each site. Necropsy procedures recommended by
the American Fisheries Society Fish Health Section (Amos
1985) were followed. The presence of abnormal growths,
lesions, or other gross changes was recorded. Liver, gonad,
and total body weights and total length were obtained for the
calculation of organosomatic indices and condition factors.
Liver somatic index (LSI) as defined by Heidinger and
Crawford (1977) was calculated as follows:

LSI = liver weight X 100 / (total weight - gonad weight)

Gonadal somatic index (GSI) was calculated as follows:

GSI = gonad weight X 100 / total weight

Condition factor (CF) was calculated as follows:

C-4

3
CF total weight X 100 / (total length)

For purposes of calculation, all weights were expressed in
grams and length was expressed in centimeters.
The term prevalence as used in this report is defined as
the proportion or percentage of individuals affected by a
certain agent or condition, i.e. the frequency of occurrence
of a condition or agent. When expressed as a proportion
prevalence will take the form:

number of fish affected / total number examined.

Bacteriology

A subsample of 20 white perch and 20 ictalurids from
each site were screened for the presence of Aeromonas
hydrophila and Flexibacter columnaris. Using a 10 jul sterile
plastic loop, inocula were taken from the lower intestine and
kidney of each fish and streaked onto RS agar (Shotts and
Rimler 1973) and Trypticase Soy Agar (TSA) for the detection
and isolation of A. hydrophila. Identification
was confirmed bio@he'mically using Roche Oxi-Ferm tubes.
Inocula from the gills of the fish were taken using 10 jul.
sterile plastic loops and streaked onto Cytophaga agar.
Colonies having the characteristics of Flexibacter columnaris
were identified with an indirect fluorescent antibody
technique using a rabbit anti-F. columnaris serum (NFRL) and
a goat anti-rabbit FITC conjugate (Gibco).

Parasitology

From each site, up to 10 individuals of each species of
fish were examined for parasites. Parasites were collected,
fixed, and preserved following the methods of Pritchard and
Kruse (1982). Trematodes, cestodes, and acanthocephalans
were fixed and preserved in Alcohol-Formalin-Acetic acid
(AFA), and were stained with Semichon's acetocarmine.
Monogeneans were fixed and preserved in 10% formalin and
mounted unstained in glycerin jelly. Nematodes were fixed
and preserved in hot 70% alcohol and mounted unstained in
glycerin jelly. Copepods were fixed and preserved in 10%
formalin and were identified from wet mounts of whole
organisms.

C@5

Histopathology

Gill and liver tissues from a subsample of 10 white
perch from each site were examined histologically. All other
white perch livers which had gross lesions were also
examined. Gill tissues from 10 ictalurids from each site,
and livers from all ictalurids collected were examined. Any
gross lesions detected during necropsy were also processed
for histological examination.
Tissues were fixed in 10% formalin, processed for
paraffin embedding, sectioned at 5 micrometers, and stained
with hematoxylin and eosin. Histologic procedures followed
were those of the Armed Forces Institute of Pathology (Luna
1968).
Tissue sections containing suspect neoplasms were
submitted to the Registry of Tumors in Lower Animals (RTLA)
in Washington, D.C. for diagnostic evaluation and
classification. Gill pathology (hyperplasia) was graded
using the system of Post (1983). Numerical grades were
assigned as follows:

0 = no hyperplasia;
1 = hyperplasia of some lamellae, no fusion of lamellae;
2 = fusing of some lamellae, primarily at distal ends of
gill filaments;
3 = most lamellae fused, no gill filaments fused;
4 = lamellae and most gill filaments fused.

Liver Enzyme Assay

Liver samples were collected from channel catfish, white
catfish and brown bullheads for AHH assay. Fish were
transported live to the laboratory, killed by a blow to the
head, and the livers were removed. Those livers that were not
assayed immediately were stored at -200 C for no longer than
one week prior to processing. A portion of liver tissue
weighing between 0.5 and 2.0 grams was homogenized in cold
Tris-sucrose buffer (pH 7.5) and the homogenate was
centrifuged for 10 minutes at 10,000 x g (Payne and Penrose,
1975).
The aryl hydrocarbon hydroxylase (AHH) activity in the
10,000 x g supernatant was measured using the method of
Nebert and Gelboin (1968). 2,5-diphenyloxazole (PPO) was
substituted for benzo[a]pyrene in the assay. PPO has been
shown to be a suitable substrate for the determination of AHH
activity in fish (Ahokas, 1976) and is safer to use than
benzo[a]pyrene, a known carcinogen (Walton et al. 1978). All
assays were performed in duplicate. A 20 juL aliquot of the
10,000 x g supernatant was added to a screw top centrifuge

C-6

tube containing 1.0 mL of the reaction mixture (0.36 pmoles
NADPH and 3 jumoles MgCl in 0.05 M Tris buffer at pH 7.5).
The tube was equilibrated in a 30 OC water bath and the
enzymatic reaction was initiated by adding 10 jug PPO (in 20
juL of methanol) to the mixture. The reaction was stopped
after 25 minutes by adding 1.0 mL of acetone.
The mixture was vortex-mixed for 30 seconds with 3.25 mL
of hexane and the phases were allowed to separate. A 2.0 mL
aliquot of the organic phase was vortex-mixed for 30 seconds
41 with 5.0 mL of 1 N NaOH. The fluorescence of the
hydroxylated PPO metabolite was measured in the alkaline
phase against a quinine sulfate standard by excitation at 345
nm and emission at 510 nm. Blank fluorescence was determined
using a duplicate set of tubes to which acetone was added
prior to the addition of PPO.
The protein content of the 10,000 x g supernatant was
determined in duplicate by the method of Lowry et al. (1951)
using bovine serum albumin as a standard. Enzyme activity is
expressed as quinine sulfate fluorescence units per milligram
of protein per 25 minutes (FU/mg protein/25 min.)

Preparation of Tissues for Toxics Analysis

Fish from the following size ranges were selected for
toxics analysis:
channel catfish between 380 and 440 mm total length,
brown bullheads between 280 and 340 mm total length,
white catfish between 280 and 340 mm total length, and
white perch between 170 and 200 mm total length.
An attempt was made to randomly select individuals from among
those collected; however, the limited availability of fish
from some sites dictated which individuals would be used, and
sometimes fish outside the desired ranges were included in
analyses. When possible five fish composites were used.
However, insufficient numbers of channel catfish from sites 3
and 6 necessitated the use of four fish composites from those
sites.
Fish used for toxics analysis were skinned and filleted
using stainless steel utensils. The fillets were cut into
cubes and homogenized into a paste in a glass container
Waring blender. Homogenized tissue was wrapped in aluminum
foil and frozen prior to submission to the analytical
laboratory. Livers were wrapped in aluminum foil directly
upon removal without homogenization. All utensils, vessels,
work surfaces, and aluminum foil were rinsed with pesticide
grade hexanes prior to their use in sample preparation.
Toxics analyses were performed by Dr. Steve Friant of
the Philadelphia Academy of Natural Sciences. Details on
analytical methods are presented in part D of this report.

C-7

Statistical Analysis

The statistical tests used to analyze data in this
report were single factor analysis of variance (ANOVA),
correlation, chi-square analysis, and Student's t-test.
A 5% significance level was set for all tests. Results of
significant tests are reported giving value of tl@e applicable
test statistic (F for ANOVA, r for regression,X' for chi-
square), degrees of freedom (df), and greatest level of
significance (either 5% or 1%, P<.05 or P<.01).

C-8

RESULTS

Gross Pathology

Gross lesions were visible on many of the fish examined.
Most were external lesions that resulted from capture by gill
nets; however, some lesions were due to other factors.
Eye pathology was a common occurrence. Individuals of
all species from all collection sites had some degree of
cloudy or opaque lenses. Since all white perch were
transported to the laboratory on ice and examined several
hours after death, it is not known whether the lens opacity
was a post-mortem change in that species. Most catfish,
however, were kept alive until examination, and cloudy lenses
were observed in some live individuals. The condition was
found to be associated.with the presence of trematode
metacercariae, Diplostomum, in the lens. The trematodes were
obserIved in both squash preparations and stained histologic
sections of the lenses. Prevalence of Diplostomum was high
in all species.
Another type of eye pathology noted was exophthalmus.
This was observed in 3 of 55 white perch from the Horseshoe
Shoals area (site 8). It appeared to be due to an
accumulation of fluid behind the eye. A bacterium, Aeromonas
hydrophila, was isolated from the fluid of two of the fish
with exophthalmus.
Internally, the most common observation was the presence
of white spots or nodules in livers of white perch. Fish from
all sites were affected. The liver nodules were examined
histologically and were diagnosed as tumors of duct cell
origin (cholangiomas). The pathology is described 'in more
detail with the results of the histopathologic examinations.
Less commonly observed abnormalities were emaciation,
ascites, lip tumors, and enlarged livers. Infectious agents
were not found associated with any of those conditions.
Emaciation occurred in a channel catfish from the Petty
Island area (site 6) and in a white perch from the Horseshoe
Shoals area (site 8). In both cases the fish had condition
factors more than 30% lower than the site mean for fish of
the same species. Digestive tracts were devoid of food
indicating anorexia. Histologically, hepatocytes were less
vacuolated than normal and liver somatic indices were 40%
lower than the mean values for that parameter.
A white perch from the Horseshoe Shoals area had a
distended abdomen filled with an ascitic fluid. No bacteria
could be cultured from the fluid on TSA.
Brown bullheads from the Paulsboro area (site 10) had
lip tumors (figure 1) diagnosed as epidermal papillomas.
Histologically, epidermal pegs from the tumors were well

C-9

A@4

--...ddmm L

B"MNIR I*T`1-7,

Figure 1. Brown%.bullhead, Ictalurus nebu'lo sus, with
epidermal papilloma.

C-10

circumscribed by a basement membrane and did not appear to
invade underlying tissues.
Several channel catfish from the Betsy Ross Bridge area
and the Petty Island area (sites 5 & 6) had enlarged, friable
livers. In those two areas, 3 of 25 (12%) of the channel
catfish were affected. The condition was not observed in
fish-from any other site.

Organosomatic Indices

Liver somatic indices, gonadal somatic indices, and
condition factors for the four species studied are presented
in tables 1-4. The gonadal somatic indices shown in the
tables were calculated from female fish only.
The liver somatic index (LSI) varied significantly
between collection sites in three of the four species; white
perch (F=91.3, P <.01), white catfish (F-29.6, P <.01), and
brown bullhead (F=3.5, P<.05). In the same three species,
mean LSI was found to be inversely correlated with water
temperatures in the period of Hay through July when
temperatures exhibited a rapid increase (water temperature
data taken from part B--Rutgers University Fish Collection
Data Report). The correlations were significant for all
three species; white perch (r=-.96, df=8, P<.01), white
catfish (r=-.97, df=4, P<.01), brown bullhead (r=-.85, df=6,
P<.01). For the same species LSI was also correlated with
dissolved oxygen levels measured at the time of sampling (see
section B). The test statistics were as follows: white perch
(r=.80, df=8, P<.01), white catfish (r=.94, df=4, P<.01), and
brown bullhead (r=.83, df=6, P<.05). The correlation between
LSI and dissolved oxygen may have been a reflection of the
LSI-temperature relationship, since temperature and dissolved
oxygen were themselves correlated in our data (r=-.69, df=8,
P<.05).
The LSI of channel catfish did not exhibit any
significant variations.
Gonadal somatic index (GSI) and observations on the
condition of the ovaries of female fish indicated when
spawning took place relative to the sampling period. White
perch spawning occurred between Hay 18 and June 18 as
reflected in the GSI which decreased from 6.02 to 1.23 during
that period. White catfish spawning appeared to have taken
place prior to May 18, as all females examined from May
through July were spent. GSI of female white catfish
remained low through the study period. Spawning of brown
bullheads did not begin until early July. Both gravid and
spent females were found in the July 9 sample from site 1.
Only gravid females were collected from the other sites,
which were sampled prior to July 9. The time of channel

C-11

TABLE 1. LIVER SOMATIC INDEX (LSI), GONADAL SOMATIC INDEX (GSI),

AND CONDITION FACTOR (CF) OF WHITE PERCH

FROM THE DELAWARE RIVER ESTUARY

SITE DATE EXAMINED LSI GSI CF

2 10-28-86 7 1.47 1.15 1.38

10 11-6-86 33 2.12 1.32 1.51

9 5-1-87 5 3.18 8.93 1.70

8 5-11-87 55 3.16 6.69 1.56

7 5-18-87 60 2.96 6.02 1.57

6 5-28-87 21 2.52 3.93 1.52

10 6-4-87 24 1.71 3.40 1.45

4 6-11-87 10 1.53 3'.10 1.40

5 6-18-87 60 1.97 1.23 1.45

3 6-29-87 34 1;,33 0.74 1.35

2 7-6-87 26 1.29 0.82 1.28

1 7-9-87 36 1.38 0.61 1.35

aw 4w, use 0" go,

milt, 4m) m ow am* vw a]* "t '40, 00 no Alo @ou, a* I" an

TABLE 2. LIVER SOMATIC INDEX (LSI), GONADAL SOMATIC INDEX (GSI),

AND CONDITION FACTOR (CF) OF CHANNEL CATFISH

FROM THE DELAWARE RIVER ESTUARY

SITE DATE EXAMINED LSI GSI CF

2 10-28-86 2 2.35 0.10 0.68

9 5-1-87 1 2.20 ---- 0.80

8 5-11-87 3 2.23 1.00 0.85

7 5-18-87 3 2.87 1.05 0.92

6 5-28-87 4 3.50 0.40 0.90

10 6-4-87 4 2.18 0.80 0.82

4 6-11-87 9 2.03 0.80 0.84

5 6-18-87 21 2.59 1.41 0.96

3 6-29-87 3 2.03 18.75 0.93

2 7-6-87 7 2.06 5.70 0.92

1 7-9-87 6 1.77 7.75 0.95

9 9-25-87 5 2.24 0.52 0.83

TABLE 3. LIVER SOMATIC INDEX (LSI), GONADAL SOMATIC INDEX (GSI),

AND CONDITION FACTOR (CF) OF WHITE CATFISH

FROM THE DELAWARE RIVER ESTUARY

SITE DATE EXAMINED LSI GSI CF

2 10-28-86 2 2.10 1.06 0.97

9 5-1-87 4 3.58 ---- 1.20

8 5-11-87 1 3.60 ---- 1.08

7 5-18-87 15 3.56 1.25 1.19

3 6-29-87 4 2.10 2.37 1.24

2 7-6-87 7 1.77 1.00 1.23

1 7-9-87 16 1.92 2.94 1.27

9 9-25-87 2 2.55 0.90 1.12

1-01, to, up, AMR aw a": Am I
am m* Im

00, 06 W 001 WK, SW (W NAW MA 140) 0*@ 90 mAlk W ift, 40 M, W,l

TABLE 4. LIVER SOMATIC INDEX (LSI), GONADAL SOMATIC INDEX (GSI)f

AND CONDITION FACTOR (CF) OF BROWN BULLHEADS

FROM THE DELAWARE RIVER ESTUARY

SITE DATE EXAMINED, LSI GSI CF

10 11-6-86 4 3.72 0.60 1.25

9 5-1-87 1 3.10 ---- 1.33

8 5-11-87 1 3.60 9.40 1.37

7 5-18-87 2 3.35 9.90 1.50

Ln
10 6-4-87 1 2.50 15.90 1.76

5 6-18-87 27 2.67 8.65 1.55

3 6-29-87 1 2.40 15.30 1.51

2 7-6-87 6 2.48 10.93 1.51

1 7-9-87 10 2.63 3.32 1.46

catfish spawning was not well defined. Both gravid and spent
females were found throughout the main sampling period (May-
July).
Condition factors (CF) of white perch exhibited
significant variation among collection sites (F=26.3, P<.01).
Since gonad weight was expected to have influenced the CF, a
possible correlation between CF and GSI was tested, and the
effect was found to be significant (r=.94, df=8, P<.01). No
variations in CF between collection sites were found for any
of the three species of catfish.

Bacteriology

Results of bacteriological screening for Aeromonas
hydrophila and Flexibacter columnaris are presented in tables
5 and 6.
Aeromonas hydrophila occurred in the intestines of fish
with an overall frequency of 72.8%. Prevalence in brown
bullheads was significantly higher than in the other species.
Prevalen2e was found to vary significantly among sampling
sites (-I =24.98, df=9, P<.01). A high frequency of
occurrence (95%) in all species collected from site 5 (Betsy
Ross Bridge area), and low frequencies at sites 6, 8 and 9
(Petty Island, Horseshoe Shoals, and mouth of Schuylkill
River) were responsible for the variation. Prevalence was
significantly correlated (r=.76 , df=8 , P<.05) with water
temperature, but not with dissolved oxygen levels.
Aeromonas hydrophila was isolated from kidneys of fish
at much lower levels. An overall prevalence of 5.0% varied
significantly among species (X2=18.7, df=3, P<.01). White
catfish were most frequently infected (17.8%), followed by
channel catfish (3.8%), white perch (2.2%), and brown
bullheads (0%). No significant differences between
collection sites were found.
Flexibacter columnaris was isolated from gills of 17% of
the fish examined. Frequency of occurrence was higher in
catfish (28%) than in white perch (10.8%). No significant
differences among collection sites were found for Flexibacter
columnaris in white perch or channel catfish. Sample sizes
of white catfish and brown bullheads were insufficient for
valid statistical analysis.

Parasitology

Results of the parasite examinations are presented in
table 7. Parasites from seven major taxonomic groups were
found. Parasites were distributed throughout the study area.

C-16

TABLE 5. PREVALENCE OF AEROMONAS HYDROPHILA FROM

INTESTINES OF FISH IN THE DELAWARE RIVER ESTUARY

WHITE WHITE BROWN CHANNEL
SITE DATE PERCH CATFISH BULLHEAD CATFISH

1 7-9-87 13/20 7/11 3/3 5/6

2 7-6-87 16/20 6/10 6/6 6/9

3 6-29-87 18/20 3/4 1/1 1/4

4 6-11-87 17/20 6/9

18/20 - 10/10 10/10
5 6-18-87

6 5-28-87 12/20 1/4

7 5-18-87 10/20 15/16 2/2 2/3

8 5-11-87 10/20 0/1 2/3

9 5-1-87 3/5 1/4 1/1

10 6-4-87 29/40 1/1 3/4

TOTALS 146/205 32/45 24/25 36/52
M (71.2) (71.1) (96 .0) (69.2)

TABLE 6. PREVALENCE OF FLEXIBACTER COLUMNARIS FROM

GILLS OF FISH IN THE DELAWARE RIVER ESTUARY

WHITE WHITE BROWN CHANNEL
SITE DATE PERCH CATFISH BULLHEAD CATFISH

1 7-9-87 2/20 5/11 2/6

2 7-6-87 1/20 0/7 1/9 1/7

3 6-29-87 4/20 3/4 0/1 0/4

4 6-11-87 4/20 4/9

0c) 5 6-18-87 2/20 3/10 4/10

6 5-28-87 2/20 3/4

7 5-18-87 1/20 1/14 0/2 1/3

8 5-11-87 2/20 0/1 0/1 0/3

9 5-1-87 1/5 0/4

10 6-4-87 2/20 1/1 2/4

TOTALS 20/185 9/41 5/24 17/50
M (10.8) (22.0) (20.8) (34.0)

TABLE 7. PREVALENCE OF PARASITES OF FISHES FROM THE

DELAWARE RIVER ESTUARY

WHITE WHITE BROWN CHANNEL
PERCH CATFISH BULLHEAD CATFISH

NUMBER EXAMINED 95 27 29 42
PARASITE

PROTOZOA
Henneguya sp. 7 2 8
Ichthyophthirius sp. 1
Trichodina sp. 1 2 12

MONOGENEA
Ligictaluridus mirabilis 11
Ligictaluridus pricei 9 3
Pterocleidus-nactus 91

TREMATODES
Allocreadium ictaluri 1
Alloglossidium geminum 1
Diplostomum sp. 86 26 28 40

CESTODES
Corallobothrium fimbriatum 17
Megathylacoides giganteum 20
Proteocephalus sp. 2

NEMATODES
Camallanus oxycephalus 6
Eustrongylides sp. 1 2

ACANTHOCEPHALA
Leptorhynchoides thecatus 5 2

COPEPODS
Ergasilus sp. 1

For the most common species of parasites, no significant
differences in prevalence between sites were observed.
Statistical analysis was not possible on parasites found at
low prevalence; however, no obvious site differences were
evident in the data. The most frequently encountered parasite
was the eye fluke, Diplostomum, which was found in the lenses
of over 90% of all fish examined. Individuals of all four
species of fish from all collection sites were infected. As
stated previously, eye flukes were associated with lens
opacity in catfish and possibly white perch.
The most common parasite of white perch was a
monogenean, Pterocleidus nactus. It was found on the gills
of 96% of the white perch examined, but not on any of the
other three species of fish.
All of the protozoans, monogeneans, and copepods were
parasitic on the gills of their hosts. A larval nematode,
Eustrongylides sp., and a cestode plerocercoid,
Proteocephalus sp., were recovered from the livers of
catfish. Diplostomum sp. infected the lens of the eye in all
four species of fish. All of the remaining parasites were
parasitic in the digestive tract of their hosts.

Histopathology

Gill pathology was evaluated on 172 fish. The most
consistent finding among all four species of fish was
hyperplasia of the lamellar epithelium. A summary of the
grading of gill hyperplasia using Post's (1983) system is
presented in table 8. Slight hyperplasia (grade 1) was
characterized by a thickening of the lamellar epithelium.
Moderate hyperplasia (grade 2) involved fusion of some
adjacent lamellae usually at the distal end of the filament
(figure 2). In fish with severe hyperplasia (grade 3) most
lamellae were fused together (figure 3). Gill hyperplasia
was least severe in channel catfish. Grade 1 hyperplasia. was
observed only in fish from sites 6, 7, 8 and 9; no
hyperplasia was observed in channel catfish from other sites.
Among the other three species of fish, grade 1 hyperplasia
was observed in fish from all sites. More extensive
hyperplasia (grades 2 & 3) was most common in brown bullhead
from sites 7, 8, 9 and 10; in white catfish from site 6; and
in white perch from site 6. There was no apparent
relationship with dissolved oxygen levels at the time of
collection. Sites where gill hyperplasia was more common
had dissolved oxygen levels that ranged from the lowest (3.5
mg/1 02 at site 10) to the highest (8.65 mg/l 0 2) levels
measured during sample collection.
Another type of gill pathology observed was a dilation
of capillaries in the gill lamellae known as lamellar
telangiectiasis (figure 4). This was observed in all four
species. Prevalence of telangiectiasis did not appear to

C-20

*all got

TABLE 8. PREVALENCE OF GILL HYPERPLASIA AMONG FOUR SPECIES OF FISH

FROM THE DELAWARE RIVER ESTUARY

WHITE WHITE BROWN CHANNEL
PERCH CATFISH BULLHEAD CATFISH

GRADE 0 NO HYPERPLASIA 5/89 9/21 10/24 30/38

GRADE I SLIGHT HYPERPLASIA 63/89 4/21 8/24 8/38

GRADE 2 MODERATE HYPERPLASIA 19/89 4/21 4/24 0/38

GRADE 3 SEVERE HYPERPLASIA 2/89 4/21 2/24 0/38

TABLE 9. PREVALENCE OF LIVER TUMORS IN WHITE PERCH

FROM THE DELAWARE RIVER ESTUARY

SITE PREVALENCE

5/40 (12.5%)

2 6/33 (18.2%)

3 7/35 (20.0%)

4 12/60 (20.0%)

5 15/60 (25.0%)

6 3/21 (14.3%)

7 9/60 (15.0%)

8 9/55 (16.4%)

9 2/5 (40.0%)

10 8/57 (14.0%)

C-22

TABLE 10. PREVALENCE OF LIVER TUMORS BY LENGTH CLASS AND

SEX OF WHITE PERCH FROM THE DELAWARE RIVER ESTUARY

PREVALENCE

LENGTH MALES FEMALES COMBINED

140-149 0/4 (0%) 0/11 (0%) 0/15 (0%)

150-159 1/23 (4%) 3/47 (6%) 4/70 (6%)

160-169 10/40 (25%) 10/91 (11%) -20/131 (15%)

170-179 5/17 (29%) 9/60 (15%) 14/77 (18%)

180-189 2/12 (17%) 11/42 (26%) 13/54 (24%)

190-199 2/9 (29%) 10/29 (34%) 12/38 (32%)

200+ 2/4 (50%) 11/30 (37%) 13/34 (38%)

TOTAL 22/109 (20%) 54/310 (17%) 76/419 (18%)

C-23

-3

Figure 2. Gills of brown bullhead with grade 2 hyperplasia,
H & E, X 100.
* WO-1

C -24

SZ-D

*001 x 'a @R H
'uTSPTdjadXlq C appj2 MqTx ppaqTTnq uAojq.10 STTT.9 *C ajnBTJ

Figure 4. Gills of channel catfish with lamellar telangiectiasis
H & E, X 100.

C-26

Figure 5. Cysts of Henneguya sp. between lamellae.of gills
of channel catfish, H & E, X 450.

C-27

:,@_--Z 77:

Irv

LAW.

Figure 6. Ligictaluridus mirabilis on gills of channel
catfish, H & E, X 450.

c-28

Figure 7. Cholangiocarcinoma (top of photo) in liver of
white perch, normal hepatocytes at bottom, H & E, X 100.

C-29

vary between sites.
Gill pathology due to parasites was minor. Henneguya
cysts in catfish gills elicited a more pronounced host
response than monogenean parasites on catfish or white perch.
Henneguya cysts occurred between gill lamellae at their bases
(figure 5), resulting in a partial obstruction of the
respiratory surface. Monogeneans (Pterocleidus nactus and
Ligictaluridus spp.) attached to the lamellae by means of
sclerotized hooks (figure 6); little or no gill damage was
observed.
Liver pathology was common in white perch. Grossly
visible nodules were observed during necropsy.
Histologically, they were determined to be of duct cell
origin (figure 7). Nodules up to 5 mm. in diameter were
observed. Specimens submitted to the @TLA were diagnosed as
cholangiomas and cholangiocarcinomas (RTLA accession Vs
3a83-3886). Ducts comprising the nodules were p-oorly to
moderately well-differentiated, mitotic figures were readily
apparent, and in some areas the tumor cells interdigitated
or invaded the surrounding normal liver tissue. Prevalence
of the liver tumors in white perch is shown in tables 9 and
10. No significant differences were found in prevalence
among collection sites or between sexes of white perch.
However prevalence did vary significantly with length of
fish (@F =26.3, df=6, P<.01). Prevalence increased
progressively with size.
Liver pathology was also observed in brown bullheads.
Sections submitted to the RTLA (RTLA accession Vs 3975,
3978, 3980) were diagnosed as foci of hepatocellular
alteration of the type believed to be incipient neoplasms.
The foci were 1.0-1.2 mm in diameter. Hepatocellular
alteration was observed in livers of 3 of 53 bullheads
examined. One fish from each of sites 2, 5, and 10 were
affected.
The only other significant liver pathology observed was in
channel catfish with grossly enlarged livers. Hepatocytes of
those fish were extensively vacuolated and in areas appeared
necrotic, suggesting fatty liver degeneration.

Liver Enzyme Assay

Hepatic AHH activity data were analyzed by single factor
analysis of variance (ANOVA) to test for differences related
to sampling location. Data from males and females were
pooled for channel catfish and white catfish. Data from male
and female brown bullheads were treated separately due to
significant sex-related differences in AHH activity (F=7.2,
P<.01). Significant differences in hepatic AHH activity were
observed among channel catfish from seven of the sampling

C-30

sites (F=2.7, P<.05, Table 11). No statistically significant
differences related to sampling location were observed in
either white catfish or brown bullhead males or females.
Results for the latter two species are listed in Table 12.
Channel catfish were also obtained from the Charles 0.
Hayford Fish Hatchery at Hackettstown, NJ for comparison.
Only channel catfish from Site 10 had hepatic AHH activities
that were significantly higher (Student's t Test; P<.05)
than the hatchery fish (AHH activity = 12.1 FU/mg protein/25
min). Some caution must be exercised in the interpretation of
the AHH activity data. Equipment problems prevented the
collection of fish samples in the fall of 1986. Therefore,
sampling was conducted during the spring and early summer of
the following year, which coincides with the spawning seasons
of the three Ictalurids. Several studies have documented
changes in hepatic AHH activities during the spawning season
(Luxon et al. 1987; Walton et al. 1978), probably related to
the role of MFO enzymes in hormone metabolism (see Koivusaari
et al. 1981). Also, Walton et al. (1978) found the hepatic
MFO system of the cunner to be less responsive to induction
by petroleum hydrocarbons during spawning.
It is not clear why AHH was higher in female brown
bullheads than in males. In other studies, AHH was found to
be lower in females than in males in pre-spawning cunner
(Walton et al. 1978), spawning lake trout (Luxon et al.
1987), and two species of sanddab (Spies et al. 1982).
Besides spawning, other factors that have been found to
affect AHH activity are body size (Stegeman, 1978),
starvation (Walton et al. 1978) and water temperature
(Stegeman, 1979). To determine whether these factors
influenced comparisons of AHH activity made in the present
study, correlations between AHH activity and the following
factors were tested: body weight, water temperature, liver
somatic index (an indicator of nutritional status) and
gonadal somatic index (an indicator of the degree of sexual
maturity in females). The degree of sexual maturity appeared
to be a significant factor in the level of AHH activity in
brown bullheads (Table 13). The hepatic AHH activity
increased with increasing gonadal-somatic index (y = O.30Ox +
9.238). In channel catfish, a significant correlation was
found between water temperature and AHH activity (y = 0.533x
+ 1.632). Body weight was correlated with AHH activity in
the white catfish (y=O.Ollx + 9.923).
AHH activity data were adjusted for temperature (channel
catfish) and body weight (white catfish) and retested for
differences among sampling sites. For channel catfish, site-
related differences in AH-H activity were no longer
statistically significant, although fish from site 10 still
exhibited the highest enzyme activity (Table 14). White
catfish AHH activity data, when adjusted for body weight,

C-31

TABLE 11. HEPATIC AHH ACTIVITIES IN CHANNEL CATFISH

FROM THE DELAWARE RIVER ESTUARY

AHH Activity
River (FU/mg Protein/25 minutes)
Site Mile n Mean (SD)

10 84.5 4 20.2 (5.5) A

2 118 8 16.7 (5.0) A B

1 120 5 13.2 (1.2) A B

5 104 6 12.8 (5.4) B

4 107 6 12.3 (4.1) B

6 102 4 10.7 (5.4) B

8 95 3 9.9 (2.7) B

3 116 2** 14.4

7 99 1** 11.4

9 92 1** 2.4

Means with the same letter are not statistically different
(two-tailed Student's t Test; alpha = 0.05)

Samples with n < 3 were not statistically analyzed.

C-32

TABLE 12. HEPATIC AHH ACTIVITIES IN WHITE CATFISH AND

BROWN BULLHEADS FROM THE DELAWARE RIVER ESTUARY

AHH Activity
River (FU/mg Protein/25 minutes)
Site Mile n Mean (SD)

White Catfish

1 120 12 15.9 (6.5)

2 118 8 16.2 (7.2)

3 116 3 13.3 (3.9)

7 99 9 11.6 (4.5)

Brown Bullhead (Males)

1 120 3 8.6 (3.9)

2 118 3 8.9 (2.8)

5 104 4 6.3 (1.5)

Brown Bullhead (Females)

1 120 4 9.7 (1.1)

2 118 3 13.1 (4.5)

5 104 11 11.2 (1.8)

C-33

TABLE. 13. CORRELATION OF HEPATIC AHH ACTIVITY TO BODY

WEIGHT, WATER TEMPERATURE, LIVER SOMATIC INDEX (LSI),

AND GONADAL SOMATIC INDEX (GSI)

Correlation Coefficients (r)

Species Water Temp. Body Wt. LSI GSI

Channel 0.368 0.150 0.275 0.305
Catfish

White 0.305 0.536* 0.289 0.305
Catfish

Brown 0.519 0.178 0.311 ND
Bullhead
(Males)

Brown 0.240 0.227 0.173 0.451
Bullhead
(Females)

Correlation coefficient statistically significant (P < 0.05)

ND - Not determined

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TABLE 14. HEPATIC AHH ACTIVITIES (TEMPERATURE CORRECTED)

IN CHANNEL CATFISH FROM THE DELAWARE RIVER ESTUARY

AHH Activity
River (FU/mg Protein/25 minutes/ 'C)
Site Mile n Mean (SD)

10 4 0.934 (0.257)

2 118 8 0.662 (0.200)

8 95 3 0.660 (0.178)

6 102 4 0.574 (0.288)

4 107 6 0.542 (0.181)

5 104 6 0.530 (0.223)

1 120 5 0.497 (0.046)

3 116 2** 0.570

7 99 1** 0.663

9 92 1** 0.179

Samples with n < 3 were not statistically analyzed.

C-35

TABLE 15. HEPATIC AHH ACTIV ITIES

(CORRECTED FOR BODY WEIGHT)

IN WHITE CATFISH FROM THE DELAWARE RIVER ESTUARY

AHH Activity
(FU/mg Protein/25 minutes/
River gram body weight)
Site Mile n Mean (SD)

7 99 8 0.073 (0.039) A*

3 116 3 0.039 (0.008) A B

1 120 12* 0.036 (0.015) B

2 118 7 0.033 (0.024) B

Means with the same letter are not statistically significant
(two-tailed Student's t Test; alpha 0.05)

C-36

exhibited significant site-related differences (F=4.3, P<.05,
table 15).
The finding of elevated AHH activities in white catfish
from Site 7 is consistent with a previous toxics study
performed in this area of the river. The sediments at Site 7
(river mile 99) were found to be contaminated with several
PAH compounds (DRBC, 1987).
No tumors were found in channel catfish in the present
study.. However, tumors were found in two brown bullheads
collected at site 10, where the highest AHH activities were
measured in channel catfish (brown bullhead liver samples
from this site were not available for measurement of hepatic
AHH activity). These observations are suggestive of exposure
to elevated levels of organic contaminants in this area.
More intensive sampling would be necessary to test this
hypothesis.

Tissue Toxics Analyses

A total of 31 tissue composites (18 muscle and 13 liver)
were submitted to the Philadelphia Academy of Natural
Sciences for toxics analyses. The results of those analyses
are presented in tables 16-19. Discussion of the results as
they relate to recommended action levels is included in the
Academy's section of this report (section D). This section
will deal only with possible relationships to observed fish
pathology.
Channel catfish with enlarged, vacuolated livers were
included in composites of.liver tissue used for toxics
analysis from sites 5 and 6. Both samples had trace metal
concentrations below or only slightly above mean values for
the seven sites from which channel catfish livers were
analyzed. For levels of PCB's, DDE, and DDD, the sample from
site 6 was well below the mean values, while the sample from
site 5 had among the highest concentrations detected. No
inference could be made concerning a possible relationship
between tissue toxicants and the observed pathology.
White perch with liver tumors were included in nine of
the ten composites of muscle tissues used for toxics
analysis as follows:
sites 5 and 10 (3 of 5 fish had grossly visible tumors),
sites 2, 3, 8, and 9 (2 of 5 fish had visible tumors),
sites 1, 4, and 6 (1 of 5 fish had visible tumors), and
site 7 (no fish had visible liver tumors).

Statistical analysis of the tissue toxics data revealed no
apparent relationship between prevalence of tumors in the
samples and toxicant levels in the muscle. Similarly,
analysis of composites of liver tissue from tumor-bearing and
grossly normal white perch provided no insight into a

C-37

possible relationship. Livers of the tumor-bearing fish had
higher levels of most metals than those of normal fish, while
the normal fish had higher levels of PCB, DDE, and DDD.

C-38

TABLE 16. TRACE METAL CONCENTRATIONS (mg/kg dry weight) IN MUSCLE TISSUE

SITE Cd Cr Cu Pb Ni Zn As Se

Channel Catfish

1 0.025 1.12 5.12 0.279 0.73 27.6 1.12 0.931

2 0.028 2.13 2.50 0.176 1.50 27.0 1.11 0.832

3 0.025 1.18 2.35 0.137 1.13 21.4 <0.60 1.08

4 0.035 1.79 4.06 0.689. 2.01 28.2 <0.60 0.849

5 0.064 2.18 6.65 0.357 2.07 24.8 <0.60 0.893

6 0.033 1.54 2.31 0.154 1.36 22.0 <0.60 0.865

9 <0.02 6.92 7.66 1.11 1.54 23.8 <0.60 1.10

White Catfish

7 0.150 2.61 61.6 3.70 3.39 53.3 <0.60 0.840

TABLE 16. CONTINUED

SITE Cd Cr Cu Pb Ni Zn As Se

White Perch

1 0.054 2.56 7.60 0.300 1.15 30.1 0.820 4.06

2 0.030 1.49 2.78 0.188 2.14 29.4 <0.60 4.56

3 0.028 3.02 5.56 0.712 2.03 30.5 0.780 3.12
C)
4 0.038 1.00 2.80 0.310 1.45 31.6 0.800 3.80
0
5 0.042 1.80 7.58 0.313 2.70 31.1 0.600 3.03

6 0.027 2.19 3.05 0.238 1.67 25.5 1.14 3.24

7 0.039 1.61 4.84 0.275 1.69 30.9 l..14 3.23

8 0.035 0.97 2.71 0.242 1.49 23.6 0.969 3.39

9 0.048 1.10 10.6 0.385 3.13 23.7 2.20 3.65

10 0.104 1.38 2.26 0.187 1.19 27.4 1.18 3.88

TABLE 17. TRACE METAL CONCENTRATIONS (mg/kg dry weight) IN LIVER TISSUE

SITE Cd Cr Cu Pb Ni Zn As Se

Channel Catfish

1 0.612 1.50 12.0 1.28 0.70 104 0.600 10.8

2 1.58 0.90 12.4 2.52 2.22 97.5 0.800 5.98

3 0.626 1.50 8.77 3.35 2.55 85.2 0.600 5.31

4 1.20 1.50 9.97 3.31 2.24 99.9 <0.60 10.4

5 0.684 0.70 6.80 2.68 0.77 65.6 <0.60 4.54

6 0.200 0.45 5.19 1.04 1.53 55.7 <0.60 5.15

9 0.496 1.63 11.5 2.69 0.30 ill <0.60 10.5

White Catfish

2 1.11 1.62 14.9 0.992 2.27 112 <0.60 13.9

7 0.594 1.28 20.9 0.787 1.98 108 <0.60 12.2

TABLE 17. CONTINUED

SITE Cd Cr Cu Pb Ni Zn As Se

Brown Bullheads

2 0.607 1.79 34.6 2.19 1.45 103 <0.60 11.6

5 0.735 1.91 36.8 1.97 2.09 110 <0.60 12.3

White Perch

5 3.65 0.53 3,089 1.35 3.96 172 1.42 119

5* 8.63 1.36 5,711 1.55 4.60 254 1.35 158

Composite sample of livers with tumors

TABLE 18. CONCENTRATIONS (mg/kg) OF PCBs, DDE, & DDD IN MUSCLE TISSUE

AROCLOR AROCLOR TOTAL
SITE 1254 1260 PCBs DDE DDD

Channel Catfish

1 3.022 1.176 4.198 1.557 0.468

2 1.336 0.217 1.553 0.464 0.258

3 2.575 1.026 3.601 0.905 0.360

4 1.718 0.626 2.344 1.454 0.440

5 2.490 0.754 3.244 2.215 0.856

5* 3.158 1.275 4.433 2.151 1.118

6 2.004 0.540 2.544 0.965 0.355

6* 2.355 0.500 2.855 0.678 0.270

9 2.522 1.022 3.544 0.940 0.372

9* 1.354 0.684 2.038 0.692 0.358

TABLE 18. CONTINUED

AROCLOR AROCLOR TOTAL
SITE 1254 1260 PCBs DDE DDD

.White Catfish

7 0.600 0.161 0.761 0.545 0.162

White Perch

1 0.315 0.094 0.409 0.144 0.045

2 <0.100 <0.100 <0.100 0.035 <0.005

3 0.285 <0.100 0.285 0.208 0.060

4 0.794 0.326 1.120 0.476 0.301

5 0.563 0.176 0.739 0.464 0.153

6 0.588 0.401 0.989 0.400 0.113

TABLE 18. CONTINUED

AROCLOR AROCLOR TOTAL
SITE 1254 1260 PCBs DDE DDD

Ln White Perch Continued

7 1.336 0.393 1.729 0.834 0.308

8 0.986 0.209 1.195 0.595 0.242

9 0.934 0.251 1.185 0.688 0.200

10 1.035 0.371 1.406 0.606 0.234

Replicate extractions

TABLE 19. CONCENTRATIONS (mg/kg) OF PCBs, DDE & DDD IN LIVER TISSUE

AROCLOR AROCLOR TOTAL
SITE 1254 1260 PCBs DDE DDD

Channel Catfish

1 0.335 <0.100 0.335 0.067 0.011

2 1.316 0.250 1.566 0.406 0.164

3 <0.100 <0.100 <0.100 0.263 0.071

4 0.538 0.226 0.764 0.280 0.087

5 1.320 0.371 1.691 0.736 0.250

5* 1.420 0.422 1.842 0.664 0.213

6 <0.100 <0.100 <0.100 0.059 0.016

9 1.427 0.938 2.365 0.152 0.076

TABLE 19. CONTINUED

AROCLOR AROCLOR TOTAL
SITE 1254 1260 PCBs DDE DDD

White Catfish

2 <0.100 <0.100 <0.100 0.118 <0.005

7 0.353 <0.100 0.353 0.200 0.062

Brown Bullheads

2 <0.100 <0.100 <0.100 <0.005 <0.005

5 0.558 0.108 0.766 0.278 0.111

White Perch

5 3.085 2.515 5.600 2.060 0.725

5** 1.516 0.569 2.085 1.527 0.438

Replicate extractions

Composite sample of livers with tumors

DISCUSSION

General Condition

Significant differences among collection sites were
detected in the measures of general condition of fish, liver
somatic index (LSI) and condition factor (CF). The
differences appear to be largely due to physiological changes
in the fish rather than to differences in environmental
quality between collection sites.
Variations in LSI among collection sites were found to
be correlated with water temperature which increased from
13.4 to 26.5 degrees Centigrade over the May-July sampling
period. Since sites were sampled at approximate one week
intervals throughout that period, water temperature
differences between sites increased up to 3 degrees C in
successive sample collections. The effect of water
temperature on LSI may have obscured any effect that might
have resulted from other differences in environmental quality
among sites. The negative correlation between LSI and water
temperature observed in this study is consistent with
previous findings of Heidinger and Crawford (1971) in
largemouth bass.
Condition factor (CF) exhibited a significant variation
among sites in white perch only. Since CF is calculated
using total body weight and total length of fish, the
relationship with gonad weight (GSI) was expected. It is
apparent in table 1 that mean CF of fish that had not yet
spawned (sites 7-9) were greater than CF of fish that were
spent (sites 1-3). Lagler (1971) indicated that all sampling
should be conducted within a single season to avoid such
variations. The lack of significant differences in the
catfish was probably due to the fact that none of those
species had a well-defined spawning period during this study.

Bacteriology

Aeromonas hydrophila occurred with a frequency of 72.8%
in Delaware River fishes, and was detected in fish from all
collection sites. The high prevalence suggests that a
substantial reservoir of infection is present and the
potential for an epizootic exists if fish become stressed.
Site differences in prevalence of Aeromonas hydrophila may
have been due in part to variations in water temperature,
since a positive correlation between temperature and
prevalence was found.
A clinical case of the disease was detected from site 8.

C-48

Aeromonas hydrophila was isolated from fluid from the eyes of
white perch exhibiting exophthalmus, which is considered a
significant clinical sign of the disease (Cipriano et al.
1984). Isolations were also made from kidneys of other fish
during the study; however, clinical signs were lacking.
Flexibacter columnaris was less prevalent than A.
hydrophila among fish in the Delaware River Estuary.
Isolation rates of F. columnaris from the gills of fish in
this study were consistent with those reported by Becker and
Fujihara (1978) from Columbia River fish collected during the
same months, and would be expected to increase as
water temperatures increased. No lesions indicative of
clinical infections were observed on gills of fish during
this study.

Parasitology

Of the sixteen parasites found during this study, only
three species may be of significant consequence to the health
of the fish stocks. Henneguya and Ichthyophthirius are
protozoan parasites which have been reported as pathogens of
channel catfish (Plumb 1985).. Although most reports involve
cultured catfish, Ichthyophthirius has been reported from
several cases of mortality in feral fish populations (Allison
and Kelly 1963; Dechtiar 1972). Pathology resulting from
Henneguya infections in this study was not considered
serious. Diplostomum has been reported as a cause of stunted
growth, abnormal feeding behavior, and reduced visual acuity
in fish (Palmeri et al. 1977), and in this study was
associated with visible cloudiness of lenses in catfish. The
effect of Diplostomum on the vision of fish has been reported
to reduce their susceptibility to angling (Moody and Gaten
1981). This effect; however, would be expected to be less
severe in catfish than in species which depend more on vision
in locating prey. No parasites that would adversely affect
appearance were found in the skin or flesh of the fish.

Idiopathic Lesions

A number of conditions observed were not associated with
any known pathogens. The most common of these were
cholangiocellular tumors in white perch. Cholangiocellular
tumors have been reported recently from white-perch from the
Chesapeake Bay by May, et al. (1987). Similar tumors have
also been reported from other species of fish (Dawe et al.
1964; Harshbarger et al. 1984) and may be associated with
high levels of polycyclic aromatic hydrocarbons (PAH) in

C-49

sediments (Baumann et al. 1987). However, the cases on which
the association is based involve bottom-feeding rather than
pelagic fish, and are from areas with sediment PAH
concentrations considerably higher than those reported for
areas within the Delaware Estuary by the Delaware River Basin
Commission (DRBC, 1987). PAH concentrations in white perch
tissues analyzed during the present study did not exceed
detection limits, although this is may be due to rapid
metabolism which has been reported to occur in fish (Eisler
1987). Other organics sampled were present in lower
concentrations in livers of tumor-bearing white perch (sample
# 4505) than in perch without tumors (sample # 4105). There
is no solid evidence linking the cholangiocellular tumors of
white perch in the present study with environmental
contaminants, although toxicants cannot be ruled out as a
possible cause. Burton and Baksi (1988) reported that the
condition of abnormal hepatic copper storage in white perch
may have contributed to the development of cholangioma in
Chesapeake Bay white perch. Using a specific stain, they
demon-strated liver changes associated with copper storage,
although tumor cells stained negatively for copper. High
levels of copper in white perch liver composites were found
in Delaware River perch and, as was the case with most of the
metals analyzed, copper levels were higher in tumor-bearing
perch than in fish without grossly visible tumors.
Environmental pollution, peribiliary fibrosis, and parasites
were other factors which Burton and Baski (1988) believed may
have contributed to the development of tumors in Chesapeake
Bay white perch.
Lip tumors (epidermal papillomas) and liver lesions
(hepatocellular alteration) were found in brown bullheads
from the Delaware Estuary. The overall prevalence of both
conditions was somewhat low; 3.8% and 5.7% respectively. Lip
tumors were found only from site 10, while bullheads from
sites 2, 5, and 10 had liver lesions. Although neither
lesion occurred frequently enough to permit statistical
analysis, bullheads from site 10 had the highest combined
prevalence of neoplastic and preneoplastic lesions.
Hepatocellular alterations are considered preneoplastic
lesions which may progress into full-blown hepatocellular
tumors (Harshbarger, pers. comm. 1987). Circumstantial
evidence exists for an association between hepatic tumors in
bullheads and PAH in sediments (Baumann et al. 1987).
Statements made previously concerning sediment toxics in the
Delaware Estuary are also applicable here. As with white
perch, detectable levels of PAH in bullhead livers were not
found in this study. The liver enzyme assays provided the
only evidence indicating a possible relationship with
exposure to environmental contaminants. Brown bullheads from
site 10 were not available for measurement of hepatic AHH
activity; however, the highest AHH activity measured in

C-50

channel catfish was in fish from site 10. This observation
is suggestive of exposure to elevated levels of organic
contaminants in that area. Additional evidence of a fish
response to elevated levels of PAH was observed in white
catfish. Elevated levels of AHH activity were observed in
fish from a site (Penns Landing area, site 7), where
sediments are contaminated with several PAH compounds (DRBC,
1987). Additional sampling of bullhead populations within
the Delaware Estuary might reveal more advanced hepatic
neoplasms and test the hypothetical relationship with PAH's.
Gill pathology constituted another common idiopathic
condition observed in fish from the Delaware Estuary.
Epithelial hyperplasia was most severe in fish from sites at
or below river mile 102 (sites 6-10). Lamellar
telangiectiasis showed no apparent differences in prevalence
or severity among sampling sites. Both epitheli al
hyperplasia and lamellar telangiectiasis have been reported
as effects of sublethal hypoxia in channel catfish (Scott and
Rogers 1980), although they are by no means pathognomonic for
hypoxia. There was no apparent relationship between gill
pathology and low dissolved oxygen levels during the present
study. Similar gill lesions may also result from external
bacterial infections (Post 1983), chemical agents (Eller
1975), and physical trauma (Herman and Meade 1985). Lamellar
telangiectiasis, in particular, may have resulted from
killing fish by a blow to the head as was the practice with
catfish in this study. The observed lack of site variations
in prevalence of lamellar telangiectiasis would be consistent
with physical trauma from sampling methods as its cause.
Emaciation, ascites, and liver enlargement were other
conditions without identifiable cause. Fish with enlarged
livers were included in several of the samples submitted for
toxicological analysis, but were not associated with elevated
levels of any of the parameters tested. Bacterial infections,
hypoxia, and environmental contaminants are among the
possible causes.
A general lack of site differences in most parameters
tested may have been due to movements of fish. Movements of
fish associated with spawning activities as well as random
movements cited in the introduction may have obscured any
real differences in parameters tested. The effect of fish
movements would be expected to be greater on chronic lesions
such as tumors than on more acute lesions such as gill
hyperplasia which, in fact, was the case.
With the exception of a relatively high prevalence of
liver tumors in white perch, the findings of this study were
not entirely unexpected. Much of the pathology observed
,might have resulted from physical stresses associated with
seasonal increases in water temperature, decreases in oxygen
levels, and the onset of spawning. Some circumstantial
evidence presented indicates that environmental contaminants

C-51

may affect the health of fish; howeverv there,is no
conclusive evidence to indicate that toxics are having a
pronounced impact on fish populations in the Delaware
Estuary.

C-52

SUMMARY

1) Two opportunistic bacterial pathogens, Aeromonas
hydrophila and Flexibacter columnari-s, were detected as part
of the normal intestinal and gill flora of fish from the
Delaware River Estuary, indicating the potential for
mortalities under conditions of environmental stress.
Prevalence of Aeromonas hydrophila was positively correlated
with water temperature and was highest at site 5. Clinical
infections of motile aeromonad septicemia were found among
white perch from site 8. Affected fish exhibited
exophthalmus. Subclinical kidney infections were detected in
white perch, white catfish, and channel catfish.

2) Sixteen species of parasites from seven major taxonomic
groups were recovered. Three parasites were considered
potential pathogens; Henneguya, Ichthyophthirius, and
Diplostomum. The eye fluke, Diplostomum, was associated with
lens opacity in catfish, and may affect visual acuity.

3) Liver tumors diagnosed as cholangiomas and
cholangiocarcinomas occurred in white perch at an overall
frequency of 18%. Prevalence increased with fish length, but
did not vary significantly among collection sites. Similar
tumors have been previously reported from bottom-feeding
fish, but only once previously in white perch, a pelagic
species. No association with environmental contaminants was
detected, although livers of tumor-bearing perch had higher
levels of most m etals than did those of grossly normal fish.

4) Lip tumors (epidermal papillomas) and liver lesions
(hepatocellular alteration) were found at low frequencies of
occurrence in brown bullheads. Liver lesions were found in
bullheads from sites 2, 5, and 10; lip tumors were found only
in bullheads from site 10. Combined prevalence for both
cond itions was highest at site 10, although small sample
sizes and low prevalence precluded valid statistical
analysis.

5) Elevated hepatic AHH activities in fish from sites 7 and
10 suggest exposure to organic (aryl hydrocarbon) contaminants
in those areas. PAH contaminated sediments were reported in
the vicinity of site 7 in a previous DRBC report. Elevated
AHH activities in fish from site 10, also the site of highest
tumor prevalence, suggests a possible link between chemical
contaminants and the occurrence of neoplasia. However,
sample sizes were too small to draw any firm conclusions.

C-53

6) Gill pathology (epithelial hyperplasia) was evident in all
four species of fish. The pathology was more severe in fish
from sites 6 through 10; and particularly in site 6. The
lesions are not characteristic of any one disease, and may
have resulted from exposure to stress in the form of hypoxia
or environmental contaminants.

7) Miscellaneous idiopathic conditions observed were emaciation,
ascites, and liver enlargement. No information was found to
support a relationship with infectious, physical, or chemical
agents.

C-54

RECOMMENDATIONS

Two of the conditions observed warrant further study:
(1) idiopathic liver tumors in white perch, and (2) tumors in
brown bullheads and their possible association with increased
AHH activity-
The occurrence of liver tumors in the whit'e perch
population follows a pattern that suggests environmental
contaminants as a possible cause. Prevalence of tumors
increased with size (age), the.tumors occurred in an organ
which functions in detoxification, and previous studies had
detected environmental contaminants in the estuary. Further
studies could test that theorized relationship by
investigating other potential causes. Electron microscopic
an d cell culture studies would serve to detect viral
involvement. Cytogenic studies could be conducted as
suggested by Dawe (1987) to determine whether a visible
chromosome anomaly is present suggesting a genetic cause.
Efforts directed toward identification of an environmental
cause would be difficult because of the mobility of the white
perch. Future studies should investigate the tumor rates and
hepatic copper levels of other populations of white perch in
coastal rivers including some "cleaner" environments, and
perhaps look at food preferences of the fish as a potential
source of environmental carcinogens.
Further studies on brown bullhead tumors should be
directed toward an intensification of sampling for that
species at sites 7 and 10 to obtain larger sample sizes.
The addition of an upstream control site is recommended.
Necropsies, histological examinations and enzyme assays
should be conducted on the fish concurrently with analysis of
sediments for PAH's. Sampling should be conducted in the
fall to eliminate the effects of spawning on AHH activity.

C-55

LITERATURE CITED

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Baumann, P.C., W.D. Smith and M. Ribick. 1982. Polynuclear
aromatic hydrocarbon (PAH) residue and hepatic tumor
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and biolo'gical chemistry. M. Cooke, A.J. Dennis and G.
Fisher, editors. Batelle Press, Columbus, OH.

Baumann, P.C., W.D. Smith and W.K. Parland. 1987. Tumor
frequencies and contaminant concentrations in brown
bullheads from an industrialized river and a recreational
lake. Trans. Amer. Fish. Soc. 116: 79-86.

Becker, C.D. and M.P. Fujihara. 1978. The bacterial pathogen
Flexibacter columnaris and its epizootiology among Columbia
River fish. AFS Monograph No. 2. 92 pp.

Bunton, T.E. and S.M. Baksi. 1988. Cholangioma in white perch
from the Chesapeake Bay. Jour. Wildlife Dis. 24:137-141.

Calhoun, A. 1966. Inland Fisheries Management. California
Department Fish & Game.

Chambers, J.E. and J.D. Yarbrough. 1976. Review: Xenobiotic
biotransformation systems in fishes. Comp. Biochem. Physiol.
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Cipriano, R.C., G.L. Bullock, and S.W. Pyle. 1984. Aeromonas
hydrophila and motile aeromonad septicemia of fish. USF&WS
Fish Disease Leaflet 68. 23 pp.

Davies, J.M. and J.S. Bell. 1984. A comparison of the levels of
hepatic aryl hydrocarbon hydroxylase in fish caught close to
and distant from North Sea oil fields. Mar. Environ. Pollut.
14: 23-45.

Dawe, C.J. 1987. Oncozoons and the search for carcinogen-
indicator fishes. Environ. Health Perspectives 71:129-137.

C-56

Dawe, C.J., M.F. Stanton, and F.J. Schwartz. 1964. Hepatic
neoplasms in native bottom-feeding fish of Deep Creek Lake,
Maryland. Cancer Research 24:1194-1199.

Dechtiar, A.0. 1972. New parasite records for Lake Erie fish.
Great Lakes Fish Commission Technical Report 17. 20 pp.

Delaware River Basin Commission. 1987. Toxics review of the
Delaware Estuary. DEL USA Project Element 16, DRBC, West
Trenton, NJ. 77 pp.

Eisler, R. 1987. Polynuclear aromatic hydrocarbon hazards to
fish, wildlife, and invertebrates: a synoptic review.
USF&WS Contaminant Hazard Reviews Report No. 11. 81 pp.

Eller, L.L. 1975. Gill lesions in freshwater teleosts. PP.
305-330 in W.E. Ribelin and G. Migaki, editors. The
Pathology of Fishes. University of Wisconsin Press,
Madison, Wisconsin. 1004 pp.

Fabacher, G. and P.C. Baumann. 1985. Enlarged livers and
hepatic microsomal mixed-function oxidase components in
tumor bearing brown bullheads from a chemically contaminated
river. Env. Tox. Chem. 4(5):703-710.

Harshbarger, J.C. 1987. Personal communication. Smithsonian
Institution Registry of Tumors diagnostic evaluations and
cover letters for accessions 3880-3890 and 3975-3980.

Harshbarger, J.C., L.J. Cullen, M.J. Calabrese, P.M. Spero,
P.C. Baumann, and W.K. Parland. 1984. Epidermal,
hepatocellular, and cholangiocellular carcinomas in brown
bullheads from industrially polluted Black River, Ohio.
Marine Env. Res. 14:535-536.

Heidinger, R.C. and S.D. Crawford. 1977. Effect of temperature
and feeding rate on the liver-somatic index of the
largemouth bass. Jour. Fish. Res. Bd. Can. 34:633-638.

Herman, R.L. and J.W. Meade. 1985. Gill lamellar dilations
(telangiectiasis) related to sampling techniques. Trans.
Amer. Fish. Soc. 114:911-913.

Koivusaari, U., M. Harri and 0. Hanninen. 1981. Seasonal variation
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Lagler, R.F. 1971. Freshwater fishery biology. Second Edition.
W.C. Brown Co., Dubuque, Iowa.

C-57

Lowry, O.H. N.J. Rosenbough, A.L. Farr an d R.J. Randall. 1951.
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Luxon, P.L., P.V. Hodson and U. Borgmann. 1987. Hepatic aryl
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MacFarlane, R.D., G.L. Bullock, and J.J. Mclaughlin. 1986.
Effects of five metals on susceptibility of striped bass to
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231.

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Moody, J. and E. Gaten. 1981. The population dynamics of eye
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pp-

Palmeri, J.R., R.A. Heckmann, and R.S. Evans. 1977. Life
history and habitat analysis of the eye fluke, Diplostomum
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Payne, J.F. and W.R. Penrose. 1975. Induction of aryl hydrocarbon
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C-58

Plumb, J A. 1985. Principal diseases of farm raised catfish.
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Plumb, J.A., J.M. Grizzle, and J. Defigueiredo. 1976. Necrosis
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Slooff, W., C.F. Van Kreijl, and A.J. Baars. 1983. Relative
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C-59

Trust, T.J., L.M. Bull, B.R. Currie, and J.T. Buckley. 1974.
Obligate anaerobic bacteria in the gastrointestinal
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1552.

C-60

PART D DATA REPORT OF ANALYSES OF

DELAWARE RIVER FISH TISSUE FOR TOXIC SUBSTANCES

ACADEMY OF NATURAL SCIENCES

TABLE OF CONTENTS

Pa@Le

INTRODUCTION .............................................. 1

METHODS ................................................... 1
Metals ............................................... 1
organics ............................................. 2

RESULTS ................................................... 3

SUN24ARY ................................................... 4

LITERATURE CITED .......................................... 5
APPENDIX ................ *,**@*:O****e**C,*,,e*,O****O**** .... 14
U.S. Environmental Prote ti n Ag n y m th d f r
the analysis of fish for cyanide.

Introduction

At the request of the Delaware River Basin Commission (DRBC)
the Academy of Natural Sciences participated in the Fish Health,
Contamination and Suitability Study of the Delaware River
Estuary. The Academy's role in this project was to analyze fish
tissue for various contaminants including trace metals, cyanide,
PCBs, selected chlorinated pesticides and polyaromatic
hydrocarbons. Phenols were originally part of the list, but
because no good analytical method for the analyses of phenols in
fish tissue exists, this parameter was dropped.
This report summarizes the results of these analyses.

Methods

Metals

Each fish tissue sample for metal analysis was prepared by
drying a 1-g piece of tissue at 600C overnight. The dried tissue
was ground, weighed and placed in a 100-ml beaker. The tissue in
the beaker was digested by adding 30 ml of concentrated nitric
acid, covering the beaker with a watch glass and heating the
sample on a hot plate at 950C for 2 h. The watch glass was then
removed and the acid evaporated to 3-5 ml. The sample was washed
from the beaker with distilled/deionized water into a 100-ml
volumetr ic flask and diluted with distilled/deionized water to
volume. Analysis was completed by flame or flameless techniques
on a Perkin Elmer Zeeman 5000 Atomic Absorption
Spectrophotometer. Acid and glassware blanks were carried
through the complete process. The concentrations of metals found
in the blanks were subtracted from the sample values. Results
are reported as mg/kg dry weight unless otherwise noted.
Fish tissue for mercury determination was prepared by
digesting 0.5 g wet weight of tissue with concentrated sulfuric

acid overnight in a waterbath at 950C. The digested tissue was
analyzed by the cold trap method as modified by Perkin Elmer
(1982).
Fish tissue for cyanide was prepared for analysis by the
EPA Method in the Appendix. Cyanide quantitation was completed by
an ion selective electrode. Because of limited sample size in
some cases, it was impossible to analyze all samples for cyanide.

organics

To facilitate sample processing within time constraints, and
to accommodate small sample size in some cases, a modification of
an EPA method was used (conversation with Larry Holland, EPA
Duluth Lab). This method permits concurrent extraction of the
sample for pesticides and polynuclear aromatics (PNAs). The
method uses Soxhlet extraction of 20 g of tissue dried with
anhydrous sodium sulfate. Each tissue sample was extracted with

350 ml of 1:1 hexane:acetone for 16 h. The extract was
concentrated to 5 ml in a Kuderna-Danish evaporator/ concentrator
with a 3-ball Snyder column. The concentrated extract was placed
on the head of a Florisil column and eluted with 50%
hexane/ether. The extract was concentrated to 2 ml for pesticide
and PCB analyses and to 0.5 ml for polyaromatic hydrocarbons.
Analyses were completed on Hewlett Packard 5890 GC. For
pesticides and PCBs a 30-m J&W 608 Megabore capillary column 608
was used. The column was operated in program temperature mode
with on-column injection, from an initial temperature of 1000C to
2750C at 80C/min, with an initial hold of 2 min. Injector port
temperature was 2250C. Carrier gas was helium at 10 ml/min. The
detector was an electrolytic conductivity detector operated in
the halogen mode.
For the analysis of PNAs a 30-m J&W DB-1 capillary column
was used. The GC was operated in the splitless injection mode
and programmed from an initial temperature of 650C to 2750C at
100/min with an initial hold of 2 min. The inlet temperature was

2750C. The detector was a HNU Systems Inc. photo-ionization
detector. Confirmation of PNAs was completed by GC/MS.

Results

The results of fish tissue analysis for trace metals are
shown in Tables 1 and 2 (all tables appear at the end of the
report). Concentrations are reported as mg/kg unless otherwise
noted. For comparison, fish metal concentrations from other
Academy studies are summarized in Table 3. The mean muscle metal
concentrations are summarized in Table 4. Mean liver metal
concentrations by species are given in Table 5. A mean was
calculated only for those metals where it was reasonable to
calculate, i.e., when most of the values were above the detection
limit. In those cases where one or two of the numbers were below
detection, a value of one-half the detection limit was used in
the calculation of the mean.
A summary of tissue concentrations for organics is given in
Table 6. Pollutants detected were PCBs, DDE and DDD. No PNAs
were detected in the tissue samples. For PCBs the major Aroclors
detected were 1254 and 1260. Channel catfish had the highest
muscle tissue concentrations (Table 6). Six of the seven channel
catfish analyzed exceeded the FDA Action Level of 2.0 ppm for
total PCB concentration. No other fish muscle tissue sample
exceeded this level. One catfish liver sample exceeded the FDA
level (1109) . For white perch two liver samples (4105, 4505)
exceeded the action level, although the corresponding tissue
samples did not. A breakdown of average muscle tissue
concentration by f ish species is shown in Table 7. Means were
calculated by using a value of one-half the detection limit. The
average tissue concentration of channel catf ish as a population
exceeded the action level while white catfish and white perch did
not. The pesticide metabolites DDE and DDD were considerably

higher in channel catf ish than in the other two species. 140
detectable PCBs were found in brown bullhead liver tissue (Table
6). The highest concentrations were found in the livers of white
perch along with higher pesticide concentrations. It should be
pointed out that in addition to PCBs, chlordane was present in
the majority of fish samples, but because of co-eluting peaks for
both compounds, it was impossible to accurately quantify the

chlordane.
The detection limits for other pesticides scanned, but not
found in fish tissue, are given in Table 9.
Polynuclear aromatics were not detectable in fish tissue.
Specific detection limits for the PNAs studied are given in Table

10.
Cyanide analysis was completed on fish samples for which a
sufficient amount of sample existed for analysis. These results
are given in Table 6.

Summary

of the metals analyzed, only antimony, thallium and
beryllium were, for the most part, below detection limits in
Delaware River fishes. Arsenic was only found in channel catfish
and white perch livers. Metal concentrations in muscle tissue
were generally comparable between channel catfish and white
perch, with the exception of selenium, which was higher in white
perch. Generally, liver concentrations of metals were highest in
white perch for arsenic, cadmium and nickel, and particularly
for copper, zinc and selenium.
For organics the highest muscle concentrations of PCBs were
found in channel catfish. of the seven samples analyzed six
exceeded the FDA Action Level. Similarly, the pesticides DDE and
DDD were highest in the muscle tissue of channel catfish.
Channel catfish liver tissue had the highest concentrations of

PCBs and pesticides. No PNAs were found in tissue samples,
possibly as a result of their rapid metabolism in the water
column by bacteria and fish.

Literature Cited

Academy of Natural Sciences of Philadelphia (ANSP). 1984a
Sabine River studies 1981-1982 for Texas Eastman Co. Rept.
No. 84-6. Acad. Nat. Sci. Phila. 166 pp.

1984b. Savannah River studies 1981-1982 in the
vicinity of the Milliken and Company plant site. Acad.
Nat. Sci. Phila. 243 pp.

1984c. Preoperational radionuclide studies for the
Susquehanna Steam Electric Station of the Pennsylvania Power
and Light Co., aquatic-terrestrial studies - 1982. Acad.
Nat. Sci. Phila. 549 pp.

1982. Preoperational radionuclide studies for the
Susquehanna Steam Electric Station of the Pennsylvania Power
and Light Co., aquatic-terrestrial studies - 1981. Acad.
Nat. Sci. Phila. 629 pp.

1981. Savannah River biological surveys, South
Carolina and Georgia, June and September 1980 for the E.I.
du Pont de Nemours and Company. Rept. No. 81-14. Acad.
Nat. Sci. Phila. 118 pp.

Friant, S.L. 1979. Trace metal concentrations in selected
biological, sediment, and water column samples in a northern
New England river. Water, Air, and Soil Pollution 11:455-
465.

Perkin Elmer Corporation. 1982. Analytical Methods for Atomic
Absorption Spectrophotometry, Norwalk, CT.

Table 1. Results of Delaware River fish muscle tissue analysis for trace metals. The first
digit of the serial number indicates the fish species as follows: I = channel cat-
fish, 2 white catfish, 3 = brown bullhead and 4 = white perch.

Dry Weight Wet Weight
(Mg/kg) (mg/kg)

Serial Cd Cr CU Pb Ni Zn As Se Sb TI Be Hg

NJD 1001 0.025 1.12 5.12 0.279 0.731 27.6 1.12 0.931 <0.5 <0.1 <0.01 0.0147
NJD 1002 0.028 2.13 2.50 0.176 1.50 27.0 1.11 0.832 <0.5 <0.1 <0.01 0.0077
NJD 1003 0.025 1.18 2.35 0.137 1.13 21.4 <0.6 1.08 <0.5 <0.1 <0.01 0.0077
NJD 1004 0.035 1.79 4.06 0.689 2.01 28.2 <0.6 0.849 <0.5 <0.1 <0.01 0.0133
NJD 1005 0.064 2.18 6.65 0.357 2.07 24.8 <0.6 0.893 <0.5 <0.1 <0.01 0.0093
NJD 1006 0.033 1.54 2.31 0.154 1.36 22.0 (0.6 0.865 <0.5 (0.1 <0.01 0.0025
NJD 1009 <0.02 6.92 7.66 1.11 1.54 23.8 <0.6 1.10 <0.5 <0.1 <0.01 0.0053
NJD 2007 0.150 2.61 61.6 3.70 3.39 53.3 <0.6 0.840 <0.5 <0.1 <0.01 0.0146
NJD 4001 0.054 2.56 7.60 0.300 1.15 30.1 0.820 4.06 <0.5 <0.1 <0.01 0.0452
NJD 4002 0.030 1.49 2.78 0.188 2.14 29.4 <0.6 4.56 <0.5 <0.1 <0.01 0.0474
NJD 4003 0.028 3.02 5.56 0.712 2.03 30.5 0.780 3.12 <0.5 <0.1 <0.01 0.0526
NJD 4004 0.038 1.00 2.80 0.310 1.45 31.6 0.800 3.80 <0.5 <0.1 <0.01 0.0195
NJD 4005 0.042 1.60 7.58 0.313 2.70 31.1 0.600 3.03 <0.5 <0.1 <0.01 0.0729
NJD 4006 0.027 2.19 3.05 0.238 1.67 25.5 1.14 3.24 <0.5 <0.1 <0.01 0.0254
NJD 4007 0.039 1.61 4.84 0.275 1.69 30.9 1.14 3.23 <0.5 <0.1 <0.01 0.0390
NJD 4008 10.035 0.97 2.71 0.242 1.49 23.6 0.969 3.39 <0.5 <0.1 <0.01 0.0306
NJD 4009 0.048 1.10 10.6 0.385 3.13 23.7 2.20 3.65 <0.5 <0.1 <0.01 0.0425
NJD 4010 0.104 1.38 2.26 0.187 1.19 27.4 1.18 3.88 <0.5 <0.1 <0.01 0.0415

Table 2. Results of Delaware River fish liver analysis for trace metals. The first digit
of the serial number indicates the fish species as follows: 1 =,-channel catfish,
2 = white catfish, 3 = brown bullhead and 4 white perch.

Dry Weight Wet Weight
(mg/kg) (mg/kg)

Serial Cd Cr Cu Pb Ni Zn As Se Sb T1 Be Hg

NJD 1101 0.612 1.50 12.0 1.28 0.70 104 0.600 10.8 (0.5 <0.1 <0.01 0.0459
NJD 1102 1.58 0.90 12.4 2.52 2.22 97.5 0.800 5.98 <0.5 <0.1 0.010 0.0223
NJD 1103 0.626 1.50 8.77 3.35 2.55 85.2 0.600 5.31 <0.5 <0.1 0.010 NS
NJD 1104 1.20 1.50 9.97 3.31 2.24 99.9 <0.6 10.4 <0.5 <0.1 0.010 0.0398
NJD 1105 0.684 0.70 6.80 2.68 0.77 65.6 <0.6 4.54 <0.5 <0.1 0.010 0.0284
NJD 1106 0.200 0.45 5.19 1.04 1.53 55.7 <0.6 5.15 <0.5 <0.1 <0.01 0.0171
NJD 1109 0.496 1.63 11.5 2.69 0.30 ill <0.6 10.5 <0.5 <0.1 <0.01 0.0321
NJD 2102 1.11 1.62 14.9 0.992 2.27 112 <0.6 13.9 <0.5 <0.1 <0.01 0.0688
NJD 2107 0.594 1.28 20.9 0.787 1.98 108 <0.6 12.2 <0.5 <0.1 <0.01 NS
NJD 3102 0.607 1.79 34.6 2.19 1.45 103 <0.6 11.6 <0.5 <0.1 <0.01 NS
NJD 3105 0.735 1.91 36.8 1.97 2.09 110 <0.6 12.3 <0.5 <0.1 <0.01 0.0177
NJD 4105 3.65 0.53 3089 1.35 3.96 172 1.42 119 <0.5 (0.1 0.018 NS
NJD 4505 8.63 1.36 5711 1.55 4.60 254 1.35 158 <0.5 M. 1 <0.01 NS

NS = No sample remaining

Table 3. concentration (mg/kg dry weight) of heavy metals in tissues Of fish collected
in 'the 1980 Savannah River survey and in other rivers of the United States by
The Academy of Natural Science's of Philadelphia.

- ---- - - ------------- - ----------------- - - - - -- - - - - ------- - ----- - -- - - ------ - - - -------- - -- - - - - - - -- - -- - ----------- - ----- ---- - -- - ----- ---- - ------------ - - - - - --------------------------
Cadmium Ckrosius Colloor Nickel Lead zinc
Alterhadv Casson It&%* to. -------- - ------ - - --- ---------- - - - ------- - - ------------------ - -- - ---- - ---- - ------- Reference
Fish %All Ranqe Rama Range r4an Range Nean Range "itan Range "talk Range
---- - ------------------------------ - -------- - --------------------------- - ------------------ - - - - ---- - --------------- - --- - -- - -------------- - -- - ---- - ---- - ---- - ------------ - - - - - - -------------- - --
Kennebec River I'veskinseed & - - (8.01 - 1 (0.01-6.0 - 0.04-1.6 - 3-41 Friant. 1919
("Ailel Stallacuth hass S - 0.15-1.67 - 1.5-6.8 - - - 0.3-0.5 - 30-39 Friant, 1979
Other (2) 6 - (0.01-0.22 - (4.01-6.1 - - 0.04-13 - 16-13 Friant, 1915

Sabine River to Blue catfish a (0.050 (0.05 0.43# (0.20-1.6 1.18 OAV-4.60 0.69 0.4-1.1 (0.40 (0.4 27.4 15.5-40.1 ANSP, 1984,
(lolls) Channel catfish & (O.Oht (4.05-6.10 US* (4.20-1.10 1.45 SAI-1.1% 0.6 4.3-0.1 1.51 (0.4-111 4112 26.7-72.2 UP. 1994A
Other M Is 0.0521 (0.050-0.10 O.295s (0.20-0.60 1.746 0.64-3.90 0.666 0.3-1.9 2.6756 (0.4-20.0 23.65 mg-i5.3 Rms?, i9eta

00 Savannah River Channel catfish 10 - 1.7# (0.05-8.50 0.46 (0.1-0.9 0.440 (0.05-1.85 (0.056 (0.05 13.1 1-21 ANSP, 1101
Meorota) Other (21 21 0.026 0.02-0.115 1.0 0.95-1.05 S.72 3.31-4.13 0.133 0.593-0.983 6.64 S.99-9.3 - - AWSP. 1994h
Other (2) 4 - 0.1651 (0.05-0.66 0.255 0.23-0.28 0.151 (0.05-0.25 (0.050 (0.05 6.0 5.0-7.0 ANSF, 1981

Susauthanna River Yellow bullhead 10 - - - - - - - ANSP. 1984C
ivennsvIvanial Blown buithead I - - 1.11 - U.7 - US, - SAt - - WS?. IME
Channel catfish 5 - - 0.92 - 9.7 1.5 16.2 AMP. 1994E
Rock bass 10 - - - - - - - ANSP, 1984c
Redbreast sonlish 5 - - 1.46 - 21.0 5.5 1.5 5 ANSP. 1984C
Pueskinseed 5 - - 1.26 - MG 2.1 0.2 "Sp. 1194C
Saallsouth bass 20 - - 0.28 0.0-4.711 16.7 7.7-38.3 21.9 2.1-73.2 0.27 0.2-0.46 ANSP. 1984c
Seallsouth bass 90 - - 0.21 0.0".738 1.041 0.144-1.680 0.861 (0.013-9.0114 0.079 (0.015-0.671 ANSF. 1982
Laroamouth bass 5 - - 5.73 28.4 3.9 31.3 ANSP. 19M
Will EfAilgill 1 9.1 2.1 1994E
Black craspis 5 0.63 37.1 0.5 17.4 ANSP. IME
Other (2) to 0.352 0.10-0.362 1.158 1.15S-1.164 0.886 0.738-1.038 0.03111 0.0276-0.051 ANSP. 198,
other (61 40 1.09 0.98-2.64 12.41 6.0-22.7 20.65 2.3-71.1 4.275 0.2-19.0 ANSF. 1984c
------------------------------ - ---------------------------------- - -- - ---------- - ---------- - ------ - -- - -------------------------- - -------- - ------ - -------------------------------- - ------ - --------------------
I - Includes at least one valat below datICtion limit.
St-.-dv area tricluded effluent of organic chemical alant.

Table 4. Mean concentrations (mg/kg dry wt, except for Hg, which is'
mg/kg wet wt) of metals in Delaware River fish muscle tissue,
by species.

Species As Cd Cr CU Hg Ni Pb Se Zn

Channel Cat. 0.53 0.03 2.41 4.38 0.0086 1.48 0.41 0.94 25
White Perch 0.99 0.04 1.71 4.98 0.0417 1.86 0.32 3.60 28

Table 5. Mean concentrations (mg/kg dry wt, except for Hg, which is
mg/kg wet wt) of metals in Delaware River fish livers, by
species.

species As Cd Cr Cu. Hg Ni Pb Se Zn

Br. Bullhead 0.30 0.67 1.85 35.7 0.0177 1.77 2.08 11.95 106
Channel Cat. 0.46 0.77 1.17 9.5 0.0309 1.47 2.41 7.53 88
White Catfish 0.30 0.85 1.45 17.9 0.0688 2.13 0.90 13.05 110
White Perch 1.39 6.14 0.95 4400 NS 4.28 1.45 139 213

NS no sample.

Table 6. Summary of tissue concentrations (mg/kg) of
organics in Delaware River fish.

Serial Aroclor Aroclor Total
Number 1254 1260 PCBa DDEb DDDb CN

1001 3.022 1.176 4.198 1.557 0.468 JC
1002 1.336 0.217 1.553 0.464 0.258 1.0
1003 2.575 1.026 3.601 0.905 0.360 JC
1004 1.718 0.626 2.344 1.454 0.440 JC
1005.1d 2.490 0.754 3.244 2.215 0.856 1C
d
1005 . 2 3.158 1.275 4.433 2.151 1.118
1006.1d 2.004 0.540 2.544 0.965 0.355 JC
1006.2d 2.355 0.500 2.855 0.678 0.270
1009.1d 2.522 1.022 3.544 0.940 0.372 JC
1009.2d 1.354 0.684 2.038 0.692 0.358
1101 0.335 0.100 0.335 0.067 0.011
1102 1.316 0.250 1.566 0.406 0.164
1103 0.100 0.100 0.100 0.263 0.071
1104 0.538 0.226 0.764 0.280 0.087
1105.1d 1.320 0.371 1.691 0.736 0.250
d
1105 . 2 1.420 0.422 1.842 0.664 0.213
1106 0.100 0.100 0.100 0.059 0.016
1109 1.427 0.938 2.365 0.152 0.076
2007 0.600 0.161 0.761 0.545 0.162 1.3
2102 0.100 0.100 0.100 0.118 0.005
2107 0.353 0.100 0.353 0.200 0.062
3102 0.100 0.100 0.100 0.005 0.005
3105 0.558 0.108 0.766 0.278 0.111
4001 0.315 0.094 0.409 0.144 0.045 ic
4002 0.100 0.100 0.100 0.035 0.005 JC
4003 0.285 0.100 0.285 0.208 0.060 JC
4004 0.794 0.326 1.120 0.476 0.301 JC
4005 0.563 0.176 0.739 0.464 0.153 1.0
4006 0.588 0.401 0.989 0.400 0.113 JC
4007 1*336 0,393 1*729 0*834 0*308 1C
4008 0.986 0.209 1.195 0.595 0.242 1.0
4009 0.934 0.251 1.185 0.688 0.200 ic
4010 1.035 0.371 1.406 0.606 0.234 1.2
4105 3.085 2.515 5.600 2.060 0.725
4505 1.516 0.569 2.085 1.527 0.438

a Detection limit for PCBs = 0.100 mg/kg.
b Detection limit for DDE and DDD 0.005 mg/kg.
c Below detection of 1 mg/kg.
d Serial numbers with decimals are replicate extractions.

Table 7. Mean concentrations (mg/kg) of organics in Delaware
River fish muscle tissue, by species.

Aroclor Aroclor Total
Species 1254 1260 PCB DDD DDE

Channel Catfish 2.253 0.782 3.035 0.486 1.202
White Catfish 0.600 0.161 0.761 0.162 0.545
White Perch 0.689 0.232 0.911 0.166 0.445

Table 8. Mean concentrations (mg/kg) of organics in Delaware
River fish livers, by species.

Aroclor Aroclor Total
Species 1254 1260 PCB DDD DDE

Brown Bullhead 0.304 0.079 0.408 0.057 0.140
Channel Catfish 0.807 0.295 1.083 0.111 0.328
White Catfish 0.202 <0.10 0.202 0.032 0.159
White Perch 2.301 1.542 3.843 0.582 1.794

Table 9. Detection limits for chlorinated pesticides in fish
tissue.

Compound Detection Limit
ug/kg

Lindanes 5
Heptachlor 5
Aldrin 5
Heptachlor epoxide 5-
Endosulfan 1 5
DDE 10
Dieldrin 10
Endrin 10
DDD 10
Endosulfan 11 10
DDT 20
Endrin aldehyde 20
Endosulfan sulfate 20

Table 10. Detection limits for PNAs in fish tissue.

Compound Detection Limit
ug/kg

Napthalene 62.5
Acenaphthylene 62.5
Acenaphthene 62.5
Fluorene 62.5
Phenanthrene 62.5
Anthracene 62.5
Fluoranthene 125
Pyrene 125
Benzo(a)anthracene 125
Chrysene 125
Benzo(b)fluoranthene 250
Benzo(k)fluoranthene 250
Benzo(a)pyrene 250
Indeno(123)pyrene 250
Dibenzo(ah)anthracene 250
Benzo(h)perylene 250

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APPENDIX
I
U.S. Environmental Protection Agency method for the analysis of
I fish for cyanide. . .
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APPENDIX

Analysis of Fish for Cyanide

1. Scope and Application

1.1 This method Is used for the determination of cyanide in fish. All
samples must be distilled prior to the analytical determination.
For cyanide levels exceeding 0.2 mg/200 ml of absorbing liquid, the
silver nitrate titrimatric method is used. For Wide levels
below this value, the calorimetric procedure is used.

2. Sample Preparation

2.1 A 5g portion of the frozen, ground fish (see "Sample Handling") is
used for the analysis. The sample should be thawed before the

analysis begins.

3. Preparation of Calibration Curve

3.T The calibration curve Is prepared from values for portions of

spiked fish tissue distilled In the manner used for the tissue

sample being analyzed. For preparation of the calibration

standards, choose and weigh a 50g portion of fish and blend in a
Waring blander (or equivalent) with 10 ml of 10% NaOH and

sufficiant deionized distilled water to bring the volume of the

mixture to 500 ml.

3.2 Using a volummtric pipet which has had the tip removed, withdraw
eight 50 ml portions and place in a series of 1 liter boiling
flasks. Sow of the flasks should be spiked with progressively
larger volumes of the cyanide standard as given In 8.7 (Method
335.2) Reference 7. Adjust the final volume of each flask to 500

ml with deionized, distilled water.

APPENDIX

3.3 Add 5O. ml of 5% NaOH solution to the absorbing tube and dilute, if
necessary,with deionized distilled water to obtain an adequate
depth Of liquid in the absorber. Coonect the boiling flask,
condenser, absorber, and trap In the train as shown In Figure I
(Method 335.2) Reference 7.
3.4 Continue with step 8.2 through 8.6 (Method 335.2) Reference 7
3.5 The calibration curve is prepared by plotting the absorbance versus
the cyanide concentration. The blank absorbance value must be
subtracted from each value before plotting the curve.

4. Sample Procedure

4.1 Place a weighed portion of the ground fish (approximately 5g) in a
blender with 100 ml of deionized, distilled water and 1 ml of 5%

NaOH solution.

4.2 Blend until a homogeneous mixture is obtained and transfer to a

T-liter boiling flask. Rinse the blander with several portions of
deionized, distilled water totaling 400 ml and add to the, boiling

flask.

4.3 Add 50ml of 5% NaOH solution to the absorbing tube and diTute if

necessary with deionized, distilled water to obtain an adequate
depth of liquid in the absorber. Connect the boiling flask,

condenser, absorber, and trap in the distillation train as shown in
Figure T (Method 335.2) and continue with step 8.2 through 8.6,

Reference T.

4.4 Read the absorbance and determine the cyanide concentration from

the calibration curve.

APPENDIX

5. Quality Assurance
5.1 Initially, demonstrate quantitative recovery with each distillation
digestion apparatus by comparing distilled aqueous standards to
non-distilled aqueous standards. Each day, distill at least one
standard to confirm distillation efficiency and purity of reagents.
5.2 At least 15% of the cyanide analyses should consist of duplicate
and spiked samples. Quality control limits should be established
and confirmed as described in chapter 5 of the "Analytical Qyality
Control Handbook," Reference 4.
6. Reporting of Data
6.1 Report cyanide concentrations as follows: less than 1.0 mg/kg, to
the nearest 0.01 mg; 1.0 mg/kg and above, to two significant
figures.
6.2 report all quality control data with the analytical resuslts for the
samples.

APPENDIZ

TABLE .1

haftclA

AU:dn
Indrft
WT "daky"
4-M HOUTIA a"- -- 4r :
C-Im . amlosaltm - I ichl", fp*=Lde
ft"VALha

umlor IM6 ftacLw =47.
Are"= AZV"= 1204 U"
&Mawr

-p -02 apkcki low a" cz-*ftrl%sz7t) otwalto
I== (4) wthrms"
I== (b)
1,12-UchLarobaname 340= Ck)
i%-=Lp#w 20 a" sea= (a) 7rmo-
Autbxacmw . 1,l*4-cwIdLLmbvmxws Ind CLZ,3-4d) 7rm*
alsoldwivk9baLaxor 2, luaw MOM= ca,h) cmbxusa*

4-eUmvehearl ;hwyt after
ether
M"kth"ftw (2-chlo2aftboxy)

4bLQv==ktbm we

Toblo ease-nautral ExtrACLAblOG

BUTI Limit of
lboxnaoloro" PotectLoa CharacteristLo Cl loull
comeound Name El ions lRel" lpt.JL fKathanal
0135 40 44(64)o 1131121 1460 148 150
0.36 40 146(1001*-148 164 113 11 1460 140: ISO
0.34 40 117(100)8 199 61 201 99 1998 2010 281
0139 44 1461100)o 140(64 s 113(111 146s 144s 150
other 0,47 40 45(100)o 77(19)o 79(12) 778 1350 137
0.95 40 225(1000 223(63 227165) 223* 225s 227
0,5$ 40 74(100)0 too(sol: 1451521 111* 143o 209
0*57 40 128(100)0 127(lO)t 1?9111) 1290 157s 16$
blo (?-cliloroothyl I other 0.61 44 93(loolf 63(9918 $5131), 630 1070 109
huX4cblorooVoIiopant4410f1Q 0064 44 237(100)t 235163); 272112) 2350 2374 239
0.64 40 77080) 133(50)0 65(15) 1240 352, 164
0,64 44 93(100): 95(321, 123(211 65 1070 137
0.76 40 162(100 164(32 0 127(31) 1610 1918 203
0.03 44 152(100 153(161t 151(171 1524 153s 181
0.86 40 154(1001s 153(951# 152(511 1540 1550 183
0107 40 624100)o 95(14)o 138118) 1390 1678 170
0.-91 40 16600810 165(80)o 1671141 1660 1670 195
0193 44 165(100)f 6317210 121(23) 1830 211. 223
1,2-dlpj%onyjby4r4xlns 0.96 40& 77000) 03(50)o 105(28) 1850 2138 225
2,4-dipitrotoluene 0.98 40 165(10010 63172)o 121(231 1838 2110 223
N-pltroso4lphonyl4mlpo 0.99 40# 169(100)o 168(711 167(501 1690 1708 190
lWX4C4lQrGb603GRG 1.00 40 284(100)o 142(30): 2491241 284s 2860 208
4-brow hopyl phopyl othor. 1.01 40 2491100)v 250199)8 141(451 249s 2510 277
plion4atcrone 1109 40. 179(100)o 179116) 176115) 1700 1790 207
opthr4cons 4,09 48 178110010 179 Ifil: 176(15 1780 1790 207
dimothyiphth4lato 1.10 40 163(100 0 16411018 194(111 Mo 163o 164
etothylplitholato 1.15 40 149(10010 178(25)0 150110) 177o 2230 251
t-luor4athano 1.23 40 202110O)s 101(23)8 100(14) 2030 231g 243
grone t.34 40 202(10010..101126)8 108(17) 2038 2310 243
d -0-bl4tylplitlialate 1.31 44 1494108)o 150(2710 104(10) 149s 2050 279
banxidina 1.34 400 194(100#92(24), 185413) 185, 2138 225
J)"tyl wozy1plith4lato 1.46 40 149(100)8 91)50) 149, 299, 327

Table I Bane-neutral extractables (Cont'44)

LLuLt ot
poteatLon CT ions
boaxone) ing) ions fRal. latti. ftthanal
Cc4UP244"d ".One
1.46 40 2291180)o 22909 1 226(23) 2208 2290 2S7
Chrysalis 1.50 40 149(188)* 1670110 3791261 149
2281100)o 229(191# 226(19) 228* -290 257
1154 48 2520 2530 281
1.66 40 2S21108)# 2531231# 1251151
1.66 40 2S21100)0 253123)0 125(16) 2520 2538 281
1.73 40 252(loo)* 253(23)# 125121) 2528 253* 261
jadaaoj1,2,3-cd)pywG48 2187 loo 276(104),p 138(28)8 277(271 2768 2770 305
2.12 too 2701100)0 139(2410 279(241 278o 279s 307
banzo(g It I)parylopa 2.16 100 27611008 138(37), 277125) 276g 2770 305

CD u-silt rosod Lmathyl itmine 42(100) 74(88)o 44(21) @d
N-attro"i-n-propylamine 130(22): 42(641* 101(12) M
t4
tj
4-chloro-phanyl pbestyl other 204(lOO)f 206 (34),j 141129)
andrin aldehy4o
loll-dichlorobanzi4ine 252(100)0 254(66)0 126(16)
2,3.7 8-tatrachloro4ibonvo-
p-dioxin 3221100)g 3201961 9(95)
his (chlorome thy 1) other 45(100)o 49(1 )g il"(5)
duuterattW anthracons (4141 1.49 40 186(loo), 94(1918 80(161 1490 217

It OP-2250 og 100/120 me4h Oupolcoport In a 61 x 2 m Id glass columns lie 0 30 al/nins
Programs 50 for 4 *in# then 11""/Ala to 26i' &M ho,14 tor 15 min.
Coo4itioning of column with base to requir*4.

Table Acid Extractables

W14it of
URT Detect on ChorACteristio C1 tons
Comeound Name 12-pitr2ehanoll (Pgf R1 Ions Mal, Int Lftethqae
Q*.63 100 128(100)8.64(5410 130(31) 1290 1314 157
0.64 1.00 94(100), 65117)8 66(19) 950 1230 135
2,4-41ahlora hGAG4 0.94 100 162(10011 164(58)0 90 611 163o 165s 167
1.00 to 0 139110010 65 (35) 8 10910) 1440 1640 122
1045 too 14211061$ 107180 * 144 32) 1438 1710 183
1,14 100 196(100)o t98(9218 2001261 1970 1990 201
a14-d1wethyl hanol 1.32 100 1221100)g 107 (901, 121 (551 1234 1510 163
1034 2 pij 184(100)o 63(59) 154153) 1950 2130 225
1442 2 pg 190(lGO)o 102(3510 77(281 1990 2278 239
Io43 100 65(100)o 139(45)g 1091721 1400 168l 122
pall, taohl.oraphe not 1.04 100 266110010 264(62)4 266(63) 2674 265j 269
daotarote4 anthrAaem 4414) 1.40 40 188000), 94(19)o 8048) 109* 217

Columns 60 glasse 2 so 1,4.
Tenaj; GC -,060188 mash
ISO - 300 0 a Min
30 *1/010

APPENDIX

Metals in Fish

Fish fillets are dried in a 60C oven. one gram of dried

muscle tissue is placed in a 100ml beaker with 30ml of Instra-

analyzed grade nitric acid, covered with a watch glass, heated

on a hot plate at 95C and refluxed for 2hrs. The digestion

solutions are evaporated until 3-5mls of acid remain, transferred
to a 100ml volumetric flask and taken to volume with 0.5% HN03'

Metal -concentrations are determined with a Perkin Elmer Model

Zeeman 5000 Atomic Absorption Spectrophotometer (Perkin Elmer,

1982).

22-

APPENDIX

BLANKS

Incorporation of blank samples (distilled water or solvent)
into the general sample pool is necessary to assess contamination
levels. Blanks for each sample container type and sample handling
procedure are introduced into the sample pool as early as
possible and analyzed at a frequency of 5% of the total number of
samples.

PRECISION, ACCURACY, CALIBRATION

For routine chemical analysis conducted In the Academy's
field or main laboratories the following QC checks applys

1. minimum of 10% replicate samples;

2. minimum of 5% spiked samples;

3. measurement of known reference solutions that are within
the range of values expected for the real samples;

4. calibration curves must have at least one blank;

5. there must be at least three (organic) or five
(inorganic) standards;

6. reference sample results must be within the acceptable
range.

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