ACUSHNET ESTUARY PCBs
DATA MANAGEMENT
FINAL REPORT
prepared for:
US Environmental Protection Agency
Region I Office of Program Support
Under Contract No. 68-04.1009
August 1983
r/EPA
w
METCALF & EDDY/ENGINEERS
BOS'O* Nt« vQf** «>ALO ALTO CMCAGO
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SECTION 1
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I’ f 7 Q _____ U.S. v. AVX Origin t lJflgaflon Documcnt
‘ __ MetcaIf&Edd j, Inc.
Engineers & Planners
50 Staniford Street
Boston, Massachusetts 02114
TWX 710321 6365
Cable METEDD-Bostori
Telex 681 7067 (METED UW)
Telephone (617) 367-4000
September 16, 1983
Mr. Robert E. Mendoza, Project Officer
Office of Program Support
U.S. Environmental Protection Agency, Region I
John F. Kennedy Federal Building
Boston, Massachusetts 02203
Dear Mr. Mendoza:
As a part of work conducted under Work Order No. 8, U.s.
EPA Contract No. 68—04—1009, it is our pleasure to submit the
attached “ACUSHNET ESTUARY PCBs DATA MANAGEMENT, FINAL REPORT.”
The PCB Data Management System was devised in response to
a need to organize a large volume of PCB related data from the
environmental measurements taken in the Acushrtet Estuary,
Massachusetts area. Based on compilation of over 5000 data
entries from twenty—three different analytical laboratories and
twenty—one different agencies, the system was used to
characterize the data for its analytical and field collection
reliability. Following the assessment for reliability, all data
were coded and entered into the system. Based on the reliable
data (over ninety percent of all the observations), analyses were
conducted to identify the type, location and extent of
contaminated areas, and delineate areas where additional data was
required. Statistical analyses of the data were also conducted
to delineate significant changes over time, as well as to
identify “hot spots” where more immediate remedial action may be
required.
This report summarizes key physical, chemical and
biological properties of PCB5 which affect their transport and
fate in the environment. Utilizing this technical foundation,
the report contains an assessment of the PCB data for use by
State and Federal regulatory agencies in the conduct of
activities related to implementation of effective remedial action
in the Acushnet Estuary area.
New York I Palo Alto / San Bernardino / Arlington Heights, IL / Chicago! Houston / Atlanta I Somerville NJ / Silver Spring / Honolulu
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R.E. Mendoza Page 2
September 16, 1983
Metcalf & Eddy, Inc., is pleased to have been a part of
the very large team of Federal, State, and rrivate agencies and
institutions that have been able to contribute to the
administrative and informational needs for effective remedial
action in the Acushnet area.
Very truly yours,
Robert J. Reimold, Ph.D
Project Manager
RJR:dmr
attachment
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PREFACE
The work described in this report was performed under Work
Order No. 8, Contract No. 68—04—1009, entitled “Preparation of
Environmental Impact Statements and NEPA Related Studies for
Region I, ” dated June 1981, between the U.S. Environmental
Protection Agency (EPA), and Metcalf & Eddy, Inc. (M&E).
This report was prepared for the Office of Program
Support, EPA, Region I. The Project Officer responsible for
overall coordination of this work was Mr. Robert E. Mendoza. The
Project Manager responsible for EPA ’s daily management of the
work was Mr. Kenneth H. Wood.
The Metcalf & Eddy, Inc. author of this report was Ms.
Elizabeth D. Eggleston. Technical support documentation and
preparation of draft material was provided by: Ms. Kathleen A.
Smith; Ms. Melanie Byrne Thomas, Mr. Paul Geoghegan, and Ms.
Christine Rosinski, Technical review of the work was conducted
by: Dr. Abu M. Z. Alam, Mr. David P. Bova, Mr. Donald M.
Brailey, Dr. Edward J. Chichon, and Mr. James G. Dedes.
Technical support related to Kriging was provided by Mr. David
Hergert and Mr. Reuel Warkov (Avco Computer Services). Dr.
Robert 3. Reimold served as Project Manager for this work; the
M&E Principal responsible for this work was Mr. Richard L. Ball,
Jr. Vice President.
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This report has been reviewed and approved for publication
by Metcalf & Eddy and the U.S. Environmental Protection Agency.
Approval does not signify that the contents necessarily reflect
the views and policies of EPA, nor does mention of trade names or
commercial products constitute endorsement or recommendation for
use.
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TABLE OF CONTENTS
Page
LETTER OF TRANSMITTAL
PREFACE
LIST OF TABLES iii
LIST OF FIGURES v
INTRODUCTION 1
SECTION 1 - LITERATURE REVIEW 5
Chemical and Physical Characteristics of PCBs 5
Physical Transformations 7
Chemical Transformations 10
Environmental Transport 1].
Transport in Air 12
Transport in Groundwater 14
Transport in Surface Water 14
Biological Processes Relevant to PCB5 18
Biodegradation 56
Bioconcentration 57
Trophic Transfer 63
Migration 65
Toxicological Effects of PCBs 66
SECTION 2 — ASSESSMENT OF THE ACUSHNET ESTUARY PCB DATA BASE 70
Data Management 70
General 70
Data Evaluation 71
Objectives 73
Data Base Assessment 73
Location and Severity of Contamination 73
Specific Contaminants Present 107
Critical Pathways and Fate Processes 114
Implications of Contamination 117
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TABLE OF CONTENTS (Continued)
Page
Effectiveness and Impacts of Potential Cleanup 120
Alternatives
REFERENCES 121
APPENDIXES
APPENDIX A — SUMMARY OF DATA MANAGEMENT FILE CONTENTS A-i
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LIST OF TABLES
Table Page
1 Physicochemical Properties of PCBs 6
2 Bioconcentration and Effects of PCBs in Estuarine
Primary Producers 19
3 Biconcentration and Effects of PCBs in Marine
Primary Producers 21
4 Bioconcentration and Effects of PCBs in
Freshwater Primary Consumers 23
5 Bioconcentration of’ Effects of PCBs in
Freshwater Secondary Consumers 211
6 Bioconcentration and Effects of PCB5 in
Freshwater Tertiary Consumers 26
7 Bioconcentration and Effects of PCBs in Estuarine
Primary Consumers 27
8 Bioconcentration and Effects of PCBs in Estuarine
Secondary Consumers 311
9 Bioconcentration and Effects of PCBs in Marine
Secondary Consumers 110
10 Bioconcentration and Effects of PCBs in Marine
Tertiary Consumers 44
11 Bioconcentration and Effects of PCBs in Avian
Primary Consumers 45
12 Bioconcentration and Effects of PCBs in Avian
Secondary Consumers 116
13 Bioconcentration and Effects of PCBs in Avian
Tertiary Consumers 147
111 Bioconcentration and Effects of PCBs in
Terrestrial Primary Consumers 53
15 Bioconcentration and Effects of PCBs in
Terrestrial Tertiary Consumers 51 1
111
METCALF & EDDY
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LIST OF TABLES (Continued)
Table Page
16 Summary of “Reliable” Data Base 7 4
17 PCB Concentrations in Inner Harbor,
Acushnet Estuary 77
18 PCB Concentrations in Outer Harbor,
Acushnet Estuary 78
19 PCB Analyses in “Reliable” Data Base 108
20 Metals Concentrations in Inner Harbor
Sediments, Acushnet Estuary 112
21 Metals Concentrations in Outer Harbor
Sediments, Acushnet Estuary 113
22 PCB Limits and Standards 118
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LIST OF FIGURES
Figure Page
1 PCB Environmental Transport Pathways 13
2 Use of Data Evaluation Criteria 72
3 Sampling Locations — Estuarine Shallow
Sediment Data 814
I Estuarine Sediment Data — Aroclor 125 4 85’
5 Color—coded Computer Graphics — Legend 87
6 Aroclor 12148 in Surface Sediments, Sampling
Locations in Upper Acushnet Estuary 88
7 Aroclor 12118 in Surface Sediments, Sampling
Locations in Middle Aoushriet Estuary 89
8 Aroclor 12514 in Surface Sediments, Sampling
Locations in Upper Acushnet Estuary 90
9 Aroclor 12514 in Surface Sediments, Sampling
Locations in Middle Acushnet Estuary 91
10 Aroclor 12514 in Shallow Sediments, Sampling
Locations in Upper Acushnet Estuary 92
11 Aroclor 12514 in Shallow Sediments, Sampling
Locations in Middle Acushnet Estuary 93
12 Arôclor 12514 in Deep Sediments, Sampling
Locations in Upper Acushnet Estuary 911
13 Aroclor 12514 in Deep Sediments, Sampling
Locations in Middle Acushnet Estuary 95
11$ Concentration Contours, Aroclor 12118 in
Surface Sediments of the Upper Acushnet
Estuary 98
15 Concentration Contours, Aroclor 12148 in
Surface Sediments of the Middle Acushnet
Estuary 99
16 Concentration Contours, Aroclor 12511 in
Surface Sediments of the Upper Acushnet
Estuary 100
V
METCALF 8 OOV
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LIST OF FIGURES (Continued)
Figure Page
17 Concentration Contours, Aroclor 125k in
- Surface Sediments of the Middle
Acushnet Estuary 101
18 Concentration Contours, Aroclor 125k in
Shallow Sediments of the Upper Acushnet
Estuary 102
19 Concentration Contours, Aroclor 125k in
Shallow Sediments of the Middle Acushnet
Estuary 103
20 Concentration Contours, Aroclor 125k in
Deep Sediments of the Upper Acushnet
Estuary 10k
21 Concentration Contours, Aroclor 12514 in
Deep Sediments of the Middle Acushnet
Estuary 105
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METCALC & EDDY
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INTRODUCTION
Ever since polychiorinated biphenyls (PCBs) were first
identified in a wide variety of environmental samples, as a bias
in pesticides analysis (Jensen, 1966), much has been written
regarding the distribution, fate and effects of these compounds
in the environment. Soon after the first published reports of
PCBs found in marine and estuarine ecosystems (Jensen et al.,
1969), it was recognized that they may pose a health hazard in
the environment. The death of over 1000 Japanese people due to
consumption of PCB contaminated rice oil (Kuratsune, 1969);
increased kit mortality in domestic mink, whose mothers had been
fed a diet including PCB containing salmon (Aulerich et al.,
1971); and the chronic toxicity of chickens exposed to a feed
room painted with paint containing a PCB binder (Gustafson,
1970), quickly focused public attention on the diverse adverse
impacts of PCBs in the environment.
In New England, an areawide survey conducted in 1976 by
the U.S. Environmental Protection Agency (EPA, 1976) first
identified PCB contamination in the Acushnet Estuary, adjacent to
New Bedford and Fairhaven, Massachusetts. High levels of PCBs
were found in a variety of environmental samples. Since that
time, extensive sampling efforts have been conducted in the
Acushnet Estuary area by numerous Federal, State, local, and
private organizations to determine the environmental fate,
effects and sources of the PCBs.
METCALF 8 EDDY
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In reviewing the industrialization of the Acushnet Estuary
area, possible sources of PCB contamination were identified.
Major users of PCBs include two electrical capacitor
manufacturers, Aerovox Incorporated and Cornell—Dubilier
Electronics Corporation, who actively discharged PCBs to the
estuary and to the municipal sewerage system from the time their
operations commenced in the 1930’s until 1977, when the use of
PCBs was banned by the U.S. EPA. Other minor users of PCBs were
also identified. Also during that time, PCB—contaminated waste
capacitors as well as dredged material from the harbor were
buried at the city landfill, an upland dump site known as
Sullivan’s Ledge, and at several other unidentified sites in the
New Bedford vicinity. Dredged materials were also used as fill
for numerous building sites throughout the city.
There is currently a pervasive PCB pollution problem
throughout the Acushriet Estuary area. Concentrations in the
sediments underlying the 985 acre harbor range from < 1 to almost
200,000 ppm (dry wt.) PCBs. Portions of Buzzards Bay are also
contaminated, with concentrations in excess of 50 ppm. Samples
taken from within the sewerage system and the municipal
wastewater treatment plant contain high PCB levels, as do air
samples in the vicinity of the sludge incinerator. Sediment,
groundwater and air PCB contamination have also been documented
at the landfill and Sullivan’s Ledge sites. In addition, a small
scale health study by the Massachusetts Department of Public
Health revealed elevated blood levels of PCBs in local residents.
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and thus became eligible for Superfund assistance. Subsequently,
a Remedial Action Master Plan (RAMP), outlining the strategy for
further sampling and investigation of cleanup alternatives was
prepared (Weston, 1983). The RAMP document summarized the
information needs, and described the actual remedial action model
and the administrative requirements, for conduct of the work.
Metcalf & Eddy, Inc.’s involvement in the Acushnet Estuary
study began in January, 1982, with an EPA Work Order (under the
U.S. EPA Region I, Office of Program Support, Mission Contract)
to institute a computerized Data Management System to handle the
large volume of PCB—related data for the Acushnet Estuary area.
This project entailed compilation of all the readily available
data; development of 30 categorical data fields to describe the
data; coding; and entering them into a computer software package
(DATATRIEvE—il). The system, described previously (Metcalf &
Eddy, Inc., 1982), is a computerized data base that has been
continuously reviewed and updated since its initiation, and
presently contains over 5000 data entries.
As an integral part of the development, implementation and
use of the data management system, numerous references to the
behavior and characteristics of PCBs, and their presence in other
ecosystems, were reviewed. This was essential to develop an
understanding of the data and a perspective as to the
identification of critical data deficiencies and prioritization
for remedial action. The objectives of this report are to:
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METCALF & EDDY
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1. summarize the comprehensive data base on contaminants
(PCBs and heavy metals) in the Acushnet Estuary
environment;
. characterize the data for use in remedial action and
resource management planning;
3. identify the type, location, and extent of highly
contaminated areas;
II. identify any critical deficiencies in the data base
that would preclude the cost—effective and timely
development and implementation of remedial action.
In order to attain these objectives, this report
summarizes selected key physical, chemical and biological
properties of PCBs which affect their transformation, transport,
fate and effects in the environment. it is not, however, a
comprehensive literature review. The report also contains an
assessment of the Acushnet Estuary PCB data base, utilizing the
above described background information to identify specific
considerations and gaps in the data. The ultimate goal of this
report, and the data management project undertaken by Metcalf &
Eddy, at the request of the U.S. EPA Region I Office of Program
Support, is to assist State and Federal agencies in the
organization, analysis, and meaningful interpretation of all
existing Acushnet Estuary PCB—related data; a necessary
prerequisite to the development of appropriate remedial actions.
METCALF & EDDY
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SECTION 1 — LITERATURE REVIEW
Chemical and Physical Characteristics of PCBs
Polychiorinated biphenyls, or PCBs, are a class of
compounds produced by the partial or complete chlorination of the
biphenyl molecule. Over 200 PCB isomers (similar molecules with
differing configurations) exist. The PCBs manufactured by
Monsanto Corporation, under the trade name Aroclor, are mixtures
of these isomers. With the exception of Aroclor 1016, the four—
digit number which follows the Aroclor name characterizes the
specific blend. The first two digits Identify the product as a
biphenyl, and the second two express the average approximate
percentage (by weight) of chlorine in the blend. Thus, Aroclor
12 12 is a biphenyl blend with approximately 42 percent chlorine
content. The only exception to this protocol is Aroclor 1016,
which Is a biphenyl blend with approximately 1 percent
chlorine. While the Aroclors containing 1 8 percent and less
chlorine are colorless mobile oils, those with higher chlorine
content are viscous liquids (Aroclor 1254) or sticky resins
(Aroclors 1260 and 1262).
The physical and chemical properties of PCBs determine the
nature and extent of’ their chemical behavior and, consequently,
the transformation and transport processes they will undergo in
the environment. The physicochemical properties of PCBs which
affect their chemical interactions are summarized in ..,le 1.
Since each Aroclor is a PCB blend, and is not a pure substance,
it will behave slightly differently depending on its specific
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TABLE 1. PHY51COCHEII CAL PtOPERTIES OF PCB.
Property
Arorlo B1 . .d
Molecular’ rang.
we Ight average
1016 —
- 1221
1232
1242 —
154—336
262
1248
222—358
268
1254
290—392
324
1260
324
370
I ChlOTtheb
41
20.5.21.3
31.4—32.5
42
4g
54
60
osaio
2 110
Vapor Presaur. (S.C)b
(jllg) ,
Vapor Preasur. (38C)
(enjlg)
14 10 4 1 t
(6.7 .1U j
i .o io j
4.06x10
—3
10
4.94i10
- 4
3.7 110
7.71i1O
6 yb
Sclub llity in wacerb
(.gI I)
0.42
115.01
(1.451
0.24
0.34
0.13
0.054
0.012
0.024
0.036
0.0027
Solubilicy in water 1
(at 20 C. pp.)
0.2
0.1
0.3
10.0231
Log Octanol/llatet
Partition Cosfficjantb
1 3
4.38
75.59
(2.eJ
4.09
13.21
4.54
4.11
3.58
(3.751
6.11
(6.031
(7.143
6.11
leery. Law coearantd
(N. at. a 3 /.ol.)
(1.4aO.7)x10
(2.7t0.5)e 1 0
(7.4i10)z10
3.7z10
(7.624.3), C1o
2.8x10 3
3
(2. 921.8) y1O
(1.410.7) 110—2
Liquid—Phi.. Maee_Tr.n.fegd
Coefficia t (1 3.10
(7.918. 3)1102
(8.7±1 .6),c10
(8. ftO.6)z10
3. 7z10
(8.328.5) 11 02
6.71102
a. liebet end Sarofin. 1972
b. Vereer. Inc.
C. All bracketed date are set i.ated.
d. Doakey and Mdr.n. 1981. inperintally and thsoratically derived data.
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MITC4LF • coo,
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composition of chlorinated biphenyl groups. The physical and
chemical properties of’ PCB isomers depend on the intramolecular
positions of substitution as well as the total chlorine content
(Callahan et al., 1979; Zitko, 1980). In evaluating
environmental samples therefore, it is important to know the
relative quantities of individual blends and isomers, in order to
permit more precise conclusions concerning their fate and
effect. Where possible, this report will distinguish between the
properties of specific isomers and those of the Aroclor blends.
Commercial PCB mixtures have been found to contain toxic
substances other than PCBs. Specifically, polychiorinated
dibenzof’urans (PCDFs) have been detected in a number of’ domestic
and foreign mixtures (EPA, 1976, 1980), as have polychiorinated
naphthalenes (PCNs) (EPA, 1980). The possibility of
polychlorinated dibenzo—p—dioxins (PCDDs) and polychiorinated
quaterphenyls (PCQs) also being present in commercial PCB
mixtures has been raised, however, there appear to be no
authenticated reports of this occurring. The potential presence
of any of’ these highly toxic compound8 in PCB mixtures
complicates both their quantification and toxicological
evaluation.
Physical Transformations
PCBs are aromatic, strongly hydrophobic compounds, (i.e.
they tend to repel water molecules), and have a low solubility in
water. In relatively non—polar organic solvents and lipids in
biological systems, PCBs are freely soluble (EPA, 1980). Water
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solubility decreases with increasing chlorination, but given that
specific PCBs are mixtures of different chlorinated biphenyl
species, the solubility is an average of the component species.
Measured and estimated PCB water solubility values range from
15.0 mg/i for Aroclor 1221 to 0.0027 mg/i for Aroclor 1260
(Callahan et al., 1979; see Table 1). The equilibrium of PCBs in
water is time—dependent, and measured values range from 2 to 5
months for the various isomers to reach equilibrium (Haque, 1980;
Rappe, 1979).
A compound’s vapor pressure influences its rate of
evaporation from environmental media. The persistance of PCBs in
soil and surface water, and their tendency to move between
environmental compartments, including the atmosphere, are highly
dependent on this chemical—specific property (Lyman et al.,
1982). The vapor pressures of PCBs are low, with values ranging
from 6.7 x atm (Aroclor 1221) to k.05 x 10 atm (Aroclor
1260) (Callahan et al., 1979; Nisbet and Sarofim, 1972).
Volatilization is the process by which a compound enters
the atmosphere as a vapor from another environmental compartment,
and it is an important mass transfer pathway from soil and
surface water to air. The rate at which a chemical volatilizes
from soil or water is affected by many factors, including the
chemical and physical properties of the compound, chemical and
physical properties of the resident media (e.g. salinity), and
environmental conditions in the overlying air. The physio—
chemical properties of PCBs cause them to be somewhat volatile
compounds, with calculated half—lives in water in the range of 9-
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12 hours (Lyman et al, 1982). Although vapor loss generally
decreases with increasing degrees of chlorination, other factors
such as the higher solubility of lower—chlorinated blends, and
any adsorbants present, greatly Influence the ultimate rate of
PCB volatilization from soil and surface water. Although the
theoretical evaporation rate of PCBs from water has been predict-
ed to be rapid, this may be limited in natural waters due to
adsorption of PCBs to sediments (EPA, 1980). Similarly, the
vapor loss of Aroclor 1251$ has been found to be appreciable from
sand, but negligible from strongly—sorbing soil surfaces (Hague,
1980)
The aromatic character of PCBs, their low water solubility
and high octanol/water partition coefficient (which represents
the tendency of’ a chemical to partition itself between an organic
phase and an aqueous phase), cause them to have a high affinity
for soil and sediment particles, especially those high in organic
matter. Adsorption of PCBs in most media increases with
decreasing water solubility and increases with the organic
content of the adsorbant (Griffin and Chian, 1980). Other
important factors affecting the adsorption coefficient are the
structural characteristics of the compound, pH of’ the medium,
particle size, and ambient temperature. Smaller particles (e.g.
clay) show a definite increase in adsorptivity of PCBs.
Adsorption reduces the volatilization rate of PCBs from water and
soil, and also reduces the tendency of PCBs to migrate in soil
and groundwater.
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Chemical Transformations
One of the characteristics of PCBs which has made them so
popular in industrial use is their extreme chemical stability.
They are inert to almost all of the typical reactions which would
change their chemical makeup. Except under extreme conditions,
PCBs do not undergo oxidation, reduction, addition, elimination,
or electrophilic substitution reactions (EPA, 1980).
The only chemical transformation process of significance
to PCBs is that of photolysis, whereby chemical decomposition is
caused by radiant energy. In aqueous systems, photolysis of PCBs
entails the replacement of chlorine with hydroxy groups (EPA,
1980). The rate of photolysis depends both on environmental
conditions (e.g. intensity and spectrum of solar radiation,
presence or absence of sensitizers) and on compound—specific
properties such as the rate and extent of light adsorption and
the inherent tendency to undergo photochemical reactions.
In the environment, anaerobic conditions enhance
photolysis (EPA, 1980). It has been demonstrated in laboratory
work (Callahan et al., 1979; Haque, 1980) that the more highly
chlorinated PCB blends are degraded to a greater extent in both
air and water than are the less chlorinated species, but whether
these results may be extrapolated to natural environmental
conditions is open to question. Photolytic dechlorination is
also expected to give rise to lower chlorinated isomers,
including some which may not have been present in the
commmercially manufactured mixtures. Under certain natural
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conditions, when the replacement of chiorines by hydroxy groups
from water, without the intervention of alkali, occur at the
ortho position, photolysis can result in the creation of
polychiorinated dlbenzofurans.
Environmental Transport
Environmental transport includes both Intermedia transfer,
(i.e. volatilization from soil to air, deposition from the water
column to the sediments) and movement within environmental
compartments, such as advective transport in estuarine f’low. For
chemically unreactive compounds such as PCBs, transport processes
are ultimately more Important than are transformation processes.
Transport of PCBs in the environment can take place by:
• volatilization from soil and surface water;
• aerial transport via particulates;
• leaching from landfills under certain conditions;
• sediment transport In rivers and estuaries;
• sediment deposition in receiving water bodies;
• uptake, bloaccuinulatlon, and transport by blota.
The transport and transfer of a chemical by each of these
pathways may Involve several sequential processes, depending on
the compartment involved. For an estuary, the principal physical
and chemical transport mechanisms would include:
• advective transport of particulate—sorbed PCBs by
flowing water;
• mixing in all directions by dispersion;
vertical transport and deposition to the sediments;
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• release from sorbed state on sediments and diffusion
into overlying water layers.
Each of these mechanisms has a characteristic rate,
diffusion velocity, and tendency to resistance (Haque, 1980).
The rates of transport nay be calculated from knowledge of the
physicochemical properties of PCBS, and the appropriate data on
atmospheric conditions, particulate transport, hydraulic
dispersion, bottom sedimentation rates, and biodegradation
rates. Since PCBs have a strong tendency to adsorb onto
particulate matter, they can be assumed, as a crude model, to
move in the same manner as sediments or atmospheric particulate
matter (Steen et al., 1978). However, the dynamics of such
properties as sorption and desorption of PCBs from particulates
are not well understood (Lyman et al., 1982). In addition, rates
of flux, including volatilization, leaching in unsaturated (with
water) soil, biodegradation in natural conditions, and diffusion
through stratified water layers are very difficult to quantify
for any compound, and are virtually unknown for PCBs.
The principal transport pathways of PCBs in the
environment are illustrated in Figure 1, and summarized below.
Transport in Air . Volatilized PCBs may be adsorbed on
particulate matter, transported by prevailing winds, and
deposited on land or water by wet and dry deposition of
particulate and vapor phase PCBs. The initial volatilization is
highly dependent on the specific isomer and the availability of
sorption sites in the resident media.
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INPUT _______________ OUTPUT
ION AIR _____________________________________ PHOTOLYSIS
VAPOR PHASE
EVAPORAT
AIR TO SURFACE
INCIN [ O 1 PARTICULATE I
DEPOSITION
I TERRESTRIAL SYSTEN DECOWOSITION
p SOILS - AND
__________________ _________________ LANDFILLS BIODEGRADATION
GROUNDWATER
BIOTA
DUWINGIBURIAL
I DREDGING AND LEACHIN( RUJO
DISPOSAL * FF OTIC FLUX
INDUSTRIAL EFFLUENT I FRESHWATER DISPERSIV MIXING
AND DISCHARGE WATER COLUM4 4
rJJNICIPAL Ids,soMd or suipended) SORPTIONIOESORPTION
SEDIMENTS I
SOURCES BIOTA DECOWOSITION
FLOW AND
I BIODEGRADATION
EFFLUENT ADVECTIVE HIVE
DISCHARGE BI IC FLUX
I _____ _______ ________ ESTUARIES DISPERSIV MIXING
WATER COLU R’J 4
(disloIved SORPTION/DESORPTION
1 SEDIMENTS 4
BIOTA 4 DEcOWOSITION
AND
BIODEGRADATION
TIDAL EXCHANGE
BIOTIC FLUX
I OCEAN iuS DISPERSIVE MIXING
WATER COLUM1 I
(di soIved or lulpendedi SORPTIONIDESORPTION
I
SEDIMENTS
L!IOTA ____________________________________ DECOWOSITION
- AND
BIODEGRADATION
FIG. 1 PCB ENVIRONMENTAL TRANSPORT PATHWAYS
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Eisenreich et al. (1980) identified airborne transport and
deposition as the major source of PCB input to the Great Lakes,
and Indicated that this pathway plays a major role in the
worldwide distribution of PCBs. Bidleman et al. (1977) estimated
the maximum vapor, particle and rain fluxes of PCBs to the
Western North Atlantic to be 1.1$ g/kin 2 /yr.
Ambient air can also act as a transport route for the
byproducts of PCB incineration. Rappe et al. (1979) found that
the pyrolysis of PCBs yielded approximately 30 major and more
than 30 minor polychiorinated dibenzofurans. One of the major
constituents was 2,3,7,8 — tetrachiorinated dibenzofuran, the
most toxic of this group of compounds. It Is evident, therefore,
that, uncontrolled incineration of PCBs can be an important
environmental source of highly toxic dlbenzofurans.
Transport in Groundwater . Experimental evidence, both
laboratory and site data, show that the mobility of PCBs in
landfill leachate is very low to negligible, due to strong
sorption to organic—rich soils (Griffin and Chian, 1980). If
landfllled PCBs were to come in contact with groundwater high in
organic content, such as seepage from a pond or a wetland,
migration of PCBs might be more significant. Likewise, the
absence of suitable soil surfaces for adsorption might increase
the likelihood of groundwater transport of PCBs.
Transport in Surface Water . When introduced to surface
water, PCBs are adsorbed to a great extent by waterborne
particulates, transported with flowing water, and diffused into
1k
-------
the sediments. Some desorption from the sediments may occur,
particularly in areas of high concentrations, but the dynamics of
this process are not well quantified at present (Haque, 1980).
Because of the high affinity of PCBs for particulate
matter, and other fate properties, the sediments in surface water
bodies are considered a sink for PCBs (Doskey and Andren, 1981;
Nisbet and Sarofim, 1982). In areas of high concentrations, PCBs
may be desorbed from the soil or sediments to pore water or the
water column, respectively, and thus constitute a continuing
sources of PCB5 to the aqueous environment (Elsenreich, 1980).
In comprehensive studies of PCB dynamics in a pond system it was
found that the sediments accumulated PCBs and released them
slowly over a period of several years, at a rate largely
controlled by the overlying water, in which PCB residence time
was only a few days with resultant volatilization (Nisbet and
Sarofim, 1972). A study in the Hudson River, north of Albany,
N.Y., revealed that PCBs from bottom sediments were released to
the river water at a constant rate during low to moderate river
flow, but rates of release were accelerated with sediment
resuspension during flood flows. It was estimated that this
sediment PCB reservoir is sufficient to maintain the current
level of water contamination in the Hudson River for
approximately one century (Turk, 1980). Similarly, Eisenreich
(1980) estimated that PCBs in surficial Lake Superior sediments
will be available for biological recycling for the next 30 to 50
years.
15
-------
Given this potentially large PCB reservoir existing in the
bottom sediments of a water body, and since PCBs exhibit a high
affinity for soil and sediment particles (especially small and/or
organic particles), sediment transport and dynamics represent the
major pathway for PCBs an estuarine environment. In a modeling
effort of PCB fate in the estuarine portion of the Hudson River
System, Thoinann et al. (1980) determined that the total PCB
concentration in the sediments was partitioned as 55 percent in
organic particulates, 20 percent in inorganic particles, and 25
percent in dissolved form. Similar work in the Great Lakes
failed to demonstrate a clear correlation between sediment PCB
concentration and either sediment texture, organic carbon
content, or redox potential (Glooschenko et al., 1976).
Due to sedimentation, differential settling velocities,
and possible stratification, the transport of pollutants adsorbed
in suspended solids does not adhere to the often—made assumption
that the pollutants move in the same manner as the water
column. Bottom sediments can also be resuspended through the
shearing action of the overlying water, and through the action of
benthic organisms that inhabit the upper layers of the bottom
sediments; a process known as bioturbatlon. Further, the
transport of PCBs cannot be fully predicted by sediment transport
dynamics alone (Nisbet and Sarofim, 1972). The suspended
materials of specific relevance to PCB transport do not
necessarily act as discrete particles, the settling velocity of
which are described by Stoke’s law. Rather, these solids
16
-------
coalesce and flocculate, and therefore require direct settling
analysis to determine the empirical settling rates in any
specific location. In addition, the sorption and exchange
dynamics of PCBs between the water column and suspended solids
are not easily quantified and are very site specific.
Studies of contaminated rivers and estuaries demonstrate
that hydrography plays an important role in the distribution of
PCBs. Downstream transport from the river to its estuary was
documented for the Hudson River, New York (Bopp et al., 1981) and
the Escambia River, Florida (Niinnio et al., 1971). In the salt—
wedge type estuary of the Duwamish River, upstream mobilization
by the more dense (saline) bottom water was well documented by
Pavion and Horn, (1979) and Pavion & Dexter, (1979). PCBs are
distributed throughout Raritan Bay (New Jersey) and the Lower
New York Bay complex (Stainken and Rollwagen, 1979) as they are
throughout Escambia Bay, Florida (Nimmo et al., 1971) due to
estuarine and riverine hydrography.
Generally, the lower chlorinated PCB blends are affected
by sediment transport and other interactions between different
elements of the aqueous environment, and therefore more subject
to movement within an estuary (Nisbet and Saroflin, 1972).
17
-------
Biological Processes Relevant to PCBs
Biological processes which can affect the fate and
transport of toxic substances in the environment include
biodegradation, bioconcentration (bloaccuinulation), trophic
transfer, and migration. Biodegradation refers to those
metabolic processes by or in an organism which result in a
breakdown in the chemical makeup of the contaminant.
Bioconcentration reflects the accumulation of the substance
within an organism. Trophic transfer refers to the passage of’
the substance in successive levels of the food chain, and
migration refers to the spatial movement of the substance in
conjunction with the movrnent of an individual organism.
Biodegradation is the only biotransformation process relevant to
PCBs, the remainder of these processes are biotransport
processes.
The chemical characteristics of PCBs which are most
significant to these biological processes are their low water
solubility, high lipid solubility, affinity for organic
particles, and extreme chemical stability. As a group, PCBs are
recalcitrant, (i.e. they resist biodegradation), and are able to
be bioconcentrated. Due to their persistence in the environment,
they can also exhibit trophic magnification; increase in
organismal concentration with trophic transfer.
There is a large volume of literature available on the
presence of PCBs in biological systems. Tables 2 through 15
18
-------
TABIZ 2.
Isomer Concen—
or tration
Aroclor (ppb )
PCB 2 7
Organiem
phytoplankton
phytoplankton
phytoplankton
phytop lanktcn
phytoplankton
phytoplankton
-a
0
Dunaltella ep .
Green flagelate
Source
water
water
water
water
water
water
water
Conditione
Loca—
Dira— tion,
tion condi—
(days) tions
1.3 St George
Sound
1.3 St George
Sound
1.3 St George
Sound
1.3 St George
Sound
1.3 St George
Sound
1.3 St George
Sound
2 Long
Inland
PcB
12112
12 1 12
1251$
1251$
pCD
Coements
30
1—2
6.5
1-2
15
5 or
10
Year
1970—
71
1970—
71
1970—
71
1970—
71
1970—
71
1970—
71
1977
:o c ThaTI0U LID or rc ii wwi anim owcns
Uptake Elimination
Terminal
Dire— concen—
Mean Range 1 tlou tration S De—
Organ (ppm) (ppm) BCF Effects (days) (ppm) crease
Inhibited
carbon
uptake
50
Toxic
Lethal
Toxic
Lethal
150 100—200 20,000 Suppressed
(lipid) growth rate
and photo—
syntheeie
50 32—70 5,000 Inhibited
(lipid) growth and
productivity
110 62—156 11,000
(lipid)
10 .011 • Lab
10 .0 14 Lab
O lorella water PCB
pyrenoidosa
Green flagellate
Chorella water TCB
pyrenoidoea HCB
Green flagellate
(dead)
1. Bioconeentration factor.
2. 31% Cl b weight.
3. 31.8% Cl by weight.
I TCB, Tetrachlorobiphenyl
MCD, Hexachiorobiphenyl.
Ref.
81$
81$
81$
811
81$
811
139
139
Steady state
Bioconcentrated
mere PCB than
celia
-------
Diatoe ,
Skeletoneuia
cO5tatua
diatom
Skeletonema
oostatum
diatos
Rhizosolenia
( ragilisalma
diatom
Cylindrotheca
cloeterium
diatom
TASL 2
Exposure Conditions
Loon-
Isomer Concen- Dura— tion,
or tration tion condi—
Source Aroclor (ppb) (days) tions
water 12511 5 2 Long
I sl nd
Sound
water 12511 0.5 2 Long 1977
Isl and
Sound
wat.r 12511 5 1 Long
Island
Sound
water 12511 10 5 Long
Island
Sound
water 1251; 7.5 5 Long 1977
Island
Sound
water 12511 1 7 Long
Is land
Sound
water 1251; 10 5 Long
Island
Sound
water 12112 100 1 St George 1970—
Sound 71
Altered
species
diversity
and size
Inhibited
chlorophyll
days
Suppressed
growth, 3.5
days
Inhibited
growth
Suppressed
growth, 3_ Il
days
Crumpled
cytoplasm,
misshapen
nucleli
1,000 Inhibited
growth
5.
oh
Particles >9 um
most sensitive
Steady state
Recovered from
suspension of
growth
Affected carbon 811
uptake
Organism
Diatoms
Diatoms
Diatoms
(Continued) • BI0 C TRATI0U AID rsu1 OF PCRe II TU&RIJ(E P1 1ThA11 PRODIJCAIS
Uptake Elimination
Terainal
Dura— concen—
Mean Range tion tration % De—
Tear Organ (ppm) (ppm) BCE Effects (days) (ppm) crease Coomenta
1977 Lethal
Ref.
10
10
100
100
10
100
100
100
(lipid)
S
-------
TAILE 3. DlO UCWRATIOU M D OF PCRa II HABIIR PUDURT PB00UC 3
Exposure Conditions Uptake Elimination
Loca— Terminal
Isomer Concen— Dura— tion, Dura— cencen—
or tration tion condi— Noan Range tion tration $ lIe—
Organism Source Aroclor (ppb) (days) tiona Year Organ (ppm) (ppm) BCF Effects (days) (ppm) crease Coents Ret.
Dunaliella water PCB 1-10 11 FF2 Increased Hixed culture. 86
tertiolecta medium competitive Nor. mensative
Green flagellate Success than pure
Dunaliella water PCB 1,000 6 FF2 85
tertiolecta carrier 10 medium
Grenn fi liete
Dunaltella water 12511 8.1 5 medium Increased Steady state 121
tertiolecta x 1o 1976 competitive reached
Green riageliate success
Dunaliella sp . water 12511 2.7 5 medium 0.25 0. 12—0.38 None Steady state 121
Grenn flagellate x I0 3 1976 (dry) reached
Dunaliella water PCB 11—25 I FF2 None Pure culture 86
terttolect.a medium
r u Green flagellate
-I
C orella water PCB S;tO 2 Long 1977 120 80—160 16000 Altered Ste ly state 10
p7renoidosa laland (lipid) (sorption) species .re ad
Green flagellate Sound diversity
and size
Thallasiosira water 12511 1 lii • FF2 1976 Diminished Steady stat. 121
pseudonana medium competitive reached
centric diatom success
Thallasiosira water PCD 25 I I Inhibited Pure culture 86
paeudonama carrier growth
centric diatom
Thallasiosira water, PCB 25— 10 FF2 Decreased 85
paeudonans carrier 100 medium growth
centric diatom
-------
Orga’ am
Thalaaaiomira
pseudonana
centric tiatem
Thalassiosira water PCB
pseudonana
centric diatom
Skeletoneam water, PCB
costatue carrier
diatom
Skeletoneea water PCB
costatum
diatom
Cocoolithus
huxleyi
0 0000litlIopore
10 2 P12
33 ppt
10 6 P/a
Raan Range
Organ (ppm) (ppm) BCF
Diminished
growth
Scee inhi—
bit.ion of
of growth
Lethal
Carbon rate 311
diminished by
1 18%
85
Carbon rate 31 1
diminished by
811%
Control 311
Year
ThBLE 3 ( etinued). DIO SC TRAT1ON lID F CTS OP PCRa II MIllIE PEDIABY PROW 3
Exposure Conditions Uptake Elimination
Loca- Terminal
Isomer Conoen— Dura— tion, Dura— concen—
or tration tion condi— tiOn tration % De—
Source Aroclor (ppb) (days ) tions Effects (days) (pps) crease
water 12511 10 5 P12 Diminished
33 ppt growth
Is.)
Coents
From Sargaaso
Sea
10 2 P/2
33 ppt
Ref.
35
water PCD 10 2 P/2
33 ppt
None
-------
I .,
.4
A
a
r
I ’
a
a
4
1\)
LA)
Expoaure
Conditiona
Uptake
Elimination
bce-
Terminal
Zeomer Concen—
Dura-
tion,
Dura—
concen—
or tration
tion
condi—
Mean
Range
tion
tratton
S LIe—
organiwa
Source
Aroclor (ppb)
(daye)
t.iona
Year
Organ (ppm)
(ppm)
BCF
Effecta (daya)
(ppm)
creaae
Commenta
Ref.
inveptebratea
water
1254
abort
term
160 —
6,300
115
Daphnia ap.
water
1248 5
InhIbited
88
water flea,
.
reproduction
adult
Raphnia .a a
water
1254 1.1
Ii
whole 52
47,000
115
water flea,
adult
Gaomarua
paeudolianaeua
water
1248 52
4
LC
91
ecud, adult
Cammarue
water
1254 1.6
7—21
whole 43
27,000
Steady atate
115
paeudoll.naeue
acud, adult
Cammarue
paeudolienaeua
water
12511 2,400
4
50
91
acud, adult
Palaemonetea
water
1254 1.3
21
whole 21.6
16,600
115
kadiakenaia
.
glana ehrl.p,
adult
Palaemonetea
kadiakeneta
water
1254 3,000
7
LC
91
gleam abrimp,
adult
Pteronarcya
water
1254 2.8
7—21
whole 7.8
2,800
Steady atate
115
doraata
atonally, larva
Culex tar.ialia
water
1254 1.5
7
whole 30
20,000
steady state
115
•oaquito, larva
-------
TABLP 5.
AID AIV i OF POPa II F VATER IIDABT SUP S
C
‘I
.4
A
r
p
a
0
0
4
t )
.
Exposure
Conditions
Uptake
Elimination
Loca-
Terminal
Isomer Concen—
1*zra— Lion,
Dura—
concen—
or tration
tion condi—
Mean Pang.
tion
tration
S 0.—
Organism Source Aroclor (ppb)
(days) Lions
Year
Organ (ppm) (ppm) BCF
Effects (days)
(ppm)
crease
Comeenta
Bet.
Orconectes flats water 12511 1.2
21
whole 6.1 5,100
115
crayfish, adult
.
Qi.oborus water 12511 1.3
I I I
whole 32.2 211,800
115
punctipennia
midge, larva
Carydalys water 12511 1.1
21
whole 7.5 6,800
Steady state
115
cornutus
dob ontly, Larva
Anguilla PCD
Canadian
1970
whole 0.71 0.36—1.01
165
roatrata
freshwater
American
eel, adult
Anguilia PCD S
Canadian
1970
liver 0.57
165
rostrata
freshwater
American
eel, adult
.
.
Phoxinus phoxinus C50
ovary 15
Significant
5
European dane,
reduction in
adult—egg
hatch
Pimephalee water 1016 8.7
32 250 C
whole 370 112,500
1118
prone las
fathead
minnow, adult
Piaepha les water 12112 5.11 —
90
Threshold
No difference
89
procelas 15.0
mortality
it parents were
fathead
(I4ATC)
exposed or not
minnow, embryo—
early juvenile
1. Colphen A 50
-------
TI LX 5 (( ntinued ) • DIO UC UTEITI UD ear OY PCRa II FU VATU SE UDA1T COUSUM IS
ExoosUre Conditions Uptake Elimination
Loca— Terminal
Isomer Concen— Dura— tion, Dura— concen—
or tration tion condi— Nean Range tion tration % De—
Organian Source Droclor (ppb) (days) tiona Tear Organ (ppa)(ppm) BCF Effecta (days) (ppm) crease Comoents Ref.
Pimephalea water 12142 whole 92 50% reduction 89
proseta s in reproductive
fathead success
minnow, adult
Pimephales water 1248 1.1 — 60 Threahold P t sensitive 23
promelas 3.0 mortality atage
fathead minnow, (HATC)
embryo-early
juvenile
Pimephales water 12148 11.0 32 25° C whole 282 70,500 1118
prc .elaa
fathead
minnow, adult
Pimephalea water - 12511 1.8 — 90 Threshold No difference 89
promela . 11.6 morality if parent, were
fathead CKATC) exposed or not
minnow, embryo—
early juvenile
Pimeohales water 12514 11.3 32 25° C whole 1130 100,000 1148
proinelaa
fathead
minnow, adult
Pimephales water 1260 1.0 32 25° C whole 1911 1911,000 1118
promelas
fathead
minnow, adult
Pimephales water 4260 2.1 — 60 Threshold 23
promelas p 1.0 mortality
fathead minnow (MA rC)
Jordanalla water 12142 whole 92 50% reduction 89
florida . in reproductive
flagfieh, adult success
-------
0 ’
Exposure
Conditions
Uptake
Elimination
Loca-
Terminal
Isomer Concen—
Ours— tion,
Dura—
concen—
or tration
tion condi—
Mean
Range
tion
tration
$ He—
organism
Source Aroclor (ppb)
(days) Lions
Year
Organ (ppm)
(ppa)
BCF
Effects
(days)
(ppm)
crease
Co enta
Ret.
Salmo trutta
water PCD 0.005
Lake
whole 5
23
brown trout
Michigan
Salmo trutta
water, PCBs 0.005
57 April—
whole 0.5
Steady eLate
23
brown trout
food 2.5
June
Salmo gairdneri
PCB
Hatchery
ovary 2.8
High
51 1
rainbow trout,
mortality
adult-eggs
of egg.
Salmo ealar
PCD
eggs 6
No harm
Anadrcmous
166
Atlantic ealmon,
lipid
to egg.
egg-fry
and fry
Salmo aalar
PCB
eggs 17
50%
Anadromoua
63
Atlantic ealmon,
mortality
egg
Salmo molar
PCB
egg
7.7—3.11
16—100%
Angdrcmous
61
Atlantic salmon,
lipid
•
egg
Pbnore eaxatili.
water, 12511 1.36
1.0 20.5—25.5°
C
whole 0.0051
2.0
<1
Anadrcmous
18
atriped bass,
acetone
2—11%
dry
larva
.
Menore eaxatili.
striped baa.,
water 12511 1.36-
0.51111
2.0 20.5-25.5°
2—4%
C
whole 0.0059
dry
2.0
0.00113
18
Steady eLate,
dry used 60%
of
18
larva
(0.952)
PCB available,
enadromous
-------
RID r is CF PCRa m IDTU&BX1IE PRDIMT N JNID3
!I
T1 .E 7.
‘U
-4
Exposure
Conditions
Uptake
Loca-
Terminal
Isomer Concen-
Airs— tion,
Dura—
concen—
or tration
tion condi—
Nean
Range
tion
tration
% De—
Organism
Source
Aroelor (ppb)
(days) tions
Tear
Organ
(ppm)
(ppm)
DCF
Et?ect.s (days)
(ppm)
crease
Comments
Ref.
Crassostrea
water
1016 10
50%
26
virginica
mortality
American oyster
Crassoatrea
water
12112 100
Toxic
26
virginica
American oyster
Crassostrea
water
12511 0.01
372
No
26
virginica
mortality
American oyster,
young adult
Crassostrea
water
12511 1
168
100
100,000
No
26
virginica
decreased
American oyster
growth
Crassostrea
water
12511 4
168
Decreased
26
virginica
growth
Dmerican oyster,
young adult
Crcs,ostrea
water
12511 4
14
Decreased
72
virginica
growth
American oyster
•
Crassostrea
water
12511 5
Tissue
26
virginica
alterations
American oyster
Crassostrea
water,
12511 1
11.0 19° C,
>8,000
19% re— I I
8.1
26
virginica
acetone
31 ppt
duotton
American oyster,
in growth
small adult
-------
Organism
Crassostrea
virginica
American oyster,
small adult
Crassomtrea
virginica
American oyster,
small adult
Crassostrea
virginica
American oyster
Crasaaomtrea
virginica
American oyster
“3
Crassoatrea
virginica
American oyster
Crasmoatrea
virginica
American oyster,
adult
Craaaotrea
virginica
Americar oyster,
adult
cramsoatrea
virginica
American oyster,
adult
TABLE 7 (Caet.Lsued).
Exposure Conditions
Loca—
Isomer Conoen— I jra— tion,
or tration Lion condi—
Source Aroelor (ppb) (days) tions
water, 1254 10 II 190 C,
acetone 31 ppt
water, 12511 100 Ii 19 C,
acetone 31 ppt
water 1254 1 30
water 1254
water 12511
water, 1254 ND Eacambia 1971
sediment <310 Bay
summer,
fall
water, 1254 ND Escambia 1972
sediment <10 Bay,
suer,
fall
water, 12511 ND Escambia 1973
sediment ND Bay
Baring 0.002
spawning
Baring 0.002
spawning
Baring 0.001
spawning
Highest concen-
tration in up-
stream sediment.
Steady state
from upstream
BIC UCIDrIATIOU AID IDT&.z a CF . m IDTU&BIIE PIIDIABY SID) S
Uptake El imina Lion
Terminal
Dura— eoncen—
Hean Range Lion tration S Be—
Tear Organ (ppm) (ppm) BCF Effects (days) (ppm) crease
>3,300 1115 re- 11 d 33.0
ducticn
in growth
Complete 21
inhibition
of growth
101,000
101,000
(max)
165,000
(max)
Comments Ref.
26
Growth resumed 26
26
72
26
162
162
162
whole 0.015
whole 0.011
whole 0.005
87
82
80
-------
TABLE 7 (Continued).
UD TECTS OF PC L I ESTIJAIXIE PIID(AJ3Y (X*ISUMESS
‘ .0
Exposure
Conditions
Uptake
-
Coaments
He r.
Organism
Isomer Conoen—
or tratlon
Source Aroolor (ppb)
Dura—
tion
(days)
Loca—
tion,
condi—
Lions
Tear
Organ
Mean Range
(ppm)
Ours—
tion
BCF Effects (days)
Terminal
coneen—
tratiOn
(ppm)
S Os—
crease
Crassostrea
virginica
American oyster
water 1,260 10
.
413% re—
duction in
growth
26
crassostrea
virginica
American oyster
Hytilum
oalitornianua
mua 5el, adult
water 1,260 300
sediment PCB 1,300
(sus-
pended)
25
•
120 C,
33 ppt
whole
800
ment dry
Lethal
threshold
167
-------
TIBLK 7 (Coettnued) • BI0Q C TRITl0I hID V&i OP PCBa II 1UIBIIE PRDURT ThI tS
Exposure Conditions Uptake Elimination
Loca- Terminal
Isomer Concen— Dura— tion, Dura— concen—
or tration tion condi— Noan Range tion tration S De—
Organism Source Aroclor (ppb) (days) tions Tear Organ (ppua) (ppm) BCF Etfecta (days) (ppm) crease Comments Ref.
Cranmon septem — aedi— 12511 >2,500 Lethal 167
spinosa , mant dry threshold
sand shrimp,
adult
commercial water 1254 <1 50 26
ahrimp
Penaeua water 12511 1 >14 Toxic 93
shrimp increased
aenaitivity to
salinity stress
Penaeua water 1254 Eacaabia 1969 whole 0_Ill 92
shrimp, adult Day
Penaeus water 1254 Eacasbia 1969 hepato— 0.6—120 92
w shrimp, adult Bay pancreas
0
Penaeua aztecus water 1016 10 LC 54 .26
brown shrimp
Penaeus duorarue water 1254 1 2 16° C, whole 0.111 140 No 26
pink shrimp, 26 ppt .ortality
juvenile
Penaeus duorarum water 1254 3 15 50$ 26
pink shrimp, mortality
juvenile
Penaeus duorarus water, 1254 3.5— 10 17° C, July— N o 26
pink shrimp, acetone 11.2 28 ppt Aug. mortality
juvenile
Penaeus duorarum water, 12511 3.5— 10— 27° C July— whole 16 1 1,156 No sy ptcma of 26
pink shrimp, acetone 11.2 20 Aug. (dead) peaticide
juvenile poisoning
-------
‘U
.1
( I
F
a
0
0
4
TABLE 7 ( mtinued) - BlO 1UC IflAfI0U LID VECT3 OP P II TU1BIIE PEDIABY IDMIS
Exposure Conditions Uptake Elimination
Loca- Terminal
Isomer Concen— I ira— tion, Dura— concen—
or tration tion condi— Mean Range tion tration S De—
Organism Source Aroclor (ppb) (days) lions Tear Organ (ppm) (ppm) BCF Effects (days) (ppm) crease Cosments Rat.
Penaeus duorarum water 1254 3.5— 20 27° C whole 33 8,571 72% 26
pink mhrSmp, acetone 4.2 28 ppt (live) mortality
juvenile July—
Aug. -
Penaau duoraru . water 1254 10 2 16° C, whole 1.3 130 No 26
pink shrimp, acetone 26 ppt mortality
juvenile
Penaeus duorarua water 12511 100 2 160 C, whole 3.9 3.9 100% 26
pink shrimp, acetone 26 ppt mortality
juvenile
Peneaus duorarum water 12511 9110 15 >50% 88
pink shriap, mortality
i s mature
Paneaua duorarum water 1254 3 35 50 % 26
pink shrimp, mortality
adult viral
intectione
Panea.j duorar , water 1254 5 20 72% 26
pink anriap mortality
adult
Peneaun duorarum water 12511 100 22 100% 26
pink shrimp mortality
Peneaus duorarum silt 12511 1,400 30 170 C hap.— 0.2 ND uptake in 93
pink shrimp, dry 27 ppt topancreas control
adult
Peneaus duorarum silt 1254 2,500 30 170 C, hepa— 1.1
pink shrimp, dry 27 ppt topanoreas
adult
-------
g
C
4
n
S
r
S
C
0
0
4
LA)
r’)
Exposure
Conditions
Uptake
Elioination
Loca-
terminal
Isomer Concen—
Dura— tion,
Ours—
concen—
or tration
tion condi—
Mean
Range
tion
tration
S Be—
Organism Source Aroclor (ppb)
(days) tton
Year
Organ (ppm)
(ppm)
5Cr
Effects
(days)
(ppm)
crease
Comments
Ret.
Peneaus duorarum silt 12511 11,900
30 170 C,
hepa— 1.3
92
pink shrimp,
27 ppt
topancreas
adult
•
Peneaua duorarum silt, 12511 30,000
30 17° C,
hepa— 6.1
92
pink shrimp dry
27 ppt
topancrea.
adult water 0.5
Peneaus duorarus sandy 1251$ 111,000
30 17° C,
hops- 6.7
ND uptake in
92
pink shrimp, silt dry
27 ppt .
topancreas
control
adult
Peneaus duorarus sandy 12511 5,700
30 170 C,
hapa- 9.8
92
pink shrimp, silt
27 ppt
topancreas
adult
Peneaus duorarun sandy 12511 61,000
30 17° C,
heps- 2110
pink shrimp, silt, dry
27 ppt
topancreas
adult water 3.5
Peneaus duorarus water 1260 100
10%
.
pink shrimp
mortality
.
fiddler crab, sand 1,2511 (2000
30 13 C,
whole 0.3±0.2
Not continuously
92
adult dry
• 27 ppt
covered with
water
Peneaus duorarum silt 12511 2,500
30 13° C,
whole 3.2*0.9
fiddler crab, dry
27 ppt
adult
Peneaus duorarum silt 12511 11,900
30 13° C,
whole 3.6±0.9
92
fiddler crab, dry
27 ppt.
adult
-------
T*RLE 7 ( eUnued) • BIOC I TflTIOI LID wi OF FCMe II IDTUIBII! FIDIAM IDM S
Ezpo ure Conditions -
Uptake
Loca-
Tereiinal
tao0er
Concan—
Our.—
tion,
Our.—
concen—
or
tratton
tion
condi—
Mean
Range
tion
tration
S 0.—
Organhan
Source
Aroolor
(ppb)
(daya)
tion.
Tear
Organ
Cppa)
(ppm)
DCF
Effecta
(day.)
(ppe)
creaae
Co cente
Ret.
fiddler crab,
.ilt
12511
30,000
30
13 C,
wIlole
17*9
adult
dry,
27 ppt
water
0.5
fiddler crab,
eandy
12511
61,000
30
13° C,
whole
8O 25
adull
eilt,
.
dry,
27 ppt
92
water
3.5
U)
U)
-------
YULE 8. BlOi*,mmjj,*UW AID V T8 OF ._ II IDTU*IIIE uAIY II 1M S
Expoaure Conditions __________________________ Elimination
Loca- Terminal
Isomer Concen- Dura— tion, Ours— concen—
or tration Lion coedi- Mean Range tion tration % De—
Organism Source Aroclor (ppb) (days) Lions Year Organ (ppm) ( ppm ) DCF Effects (day,) (ppm) crease Comment, Ref.
t allinectes water, 1254 3.5 — 20 280 C whole 23 18—27 5,9711 7.0 22 11 26
sapidus , acetone 11.2 27 ppt (10—37)
blue crab, Aug. —
Juvenile Sept.
Callinectes water, 12511 28° C whole 23 18—27 28 11 52 26
sapidun , acetone 27 ppt (3—111)
blue crab, Aug. —
Juvenile Sept.
Callineotes water 12511 5 20 8 4,000 not 26
sapidue , affected
blue crab, adult
fishes water 1016 28 3,400 Steady stata 117
(max)
(a) fishes watar 12511 28 3,700 Steady state 47
(max)
Anguilla PCB St. 1975 edible 3.0 Catadromous 41
roatrata , Lawrence
american eel, River
small adult
(<2.5 lbs.)
Anguilla PCB St. . 1975 edible 8.2 Catadrommus I I I
roatrata Lawrence
American eel, River
medium adult
(2.5—4.5 lbs.)
Angujila PCB St. 1975 edible 12.11 Catadromous
rostrata Lawrence
American eel, River
large adult
(>4.5 lbs.)
-------
LID OF FC II IDTULRIIE xuLRY I I S
1 l..in.Iu4 ,n
TL .E 8 (Continued).
U,
U’
Exposure
Conditions
Uptake
Loca -
-
Terminal
Isomer Cocoon—
Ours— Lion,
Dura—
concen—
or tration
Lion condi—
Mean
Range
Lion
tration
% De—
Organism
Source
Aroolor (ppb)
(days) tions
Year
Organ
(ppm)
(ppm)
BCP
Effects
(days)
(ppm)
crease
Cosments
Ref.
Fundulu.
water
1221 25
85S
heteroc litu 5
mortality
26
killifish
.
Cyperinodon
water
1016 0.3
28
eggs
3
10,000
no effect
46
variegatua
on fry
aheepahead
minnow, adult—
eggs
Cyperinodon
water
1016 3
28
eggs
7
2,333
no effect
116
variegatun
Cfl fry
aheepahead
minow, adult—
• n
•
Cyperinodon
water
1016 (10
28
2,500-
not
variegatus
8,100
affected
aheepshead
minnow
Cyperinodon
water
1016 32—100
28
died
variegatus
26
aheepshead
minnow
•
Cyperinodon
water
1016 15
)14
lethal
variegatus
116
mhoepshead
minnow, try
Juvenile, or
adult
Cypartnodon
variegatus
water
1254 0.1
LC 50
MeSt sensitive
Satuarin.
26
mheepehsad
organism
minnow, fry
tested
-------
TABLE 0 (Coetinued).
AID V! ,U CF. II IDTUABIIE SEC DIBT ISUPID3
U)
0
Exposure
Conditions
Uptake
Elimination
Cosmenta
Rat.
Organism Source
Isomer
or
Aroclor
Concen—
tration
(ppb)
Dura—
tion
(days)
Loca-
tion,
condi—
Lions
Tear
Organ
Hean
(ppm)
Rang.
(ppm)
BCF
Ours—
tion
Effects (days)
Terminal
concen—
tration
(ppm)
S Os—
crease
Cyperinodon water
variegatus
aheepshead
minnow, fry
12514
3
(14
.
lethal
26
Cyperinodon water
variegatus
sheepshead
minnow, Juvenile
1254
0.1
>14
lethal
to some
118
Cyperinodon water
variegatus
eheepahead
minnow, Juvenile
12514
5
>111
lethal
118
Cyperinodon water
variegatus
sheepshead
minnow, adult-egg
125j
0.1
28
eggs
>5
decreased
survival of
try, w,—
affected adults
.
115
Lagodon water
rhomboidee,
pinfish
1016
15
‘
>111
lethal
145
L.angodon water
rhomboidea.
pinfish
1016
21
1 12 •
1.1
11,000—
211,000
significant
mortality
26
Langodon water
rhoaboidee ,
pinfiab
1016
32
42
0.34
11,000—
24,000
significant
mortality,
liver alterations
26
Lagodon water
rhosboides,
pinfish
1016
100
Ii
18% mortality
26
-------
Organism Source
Lagodon water
rhoinboide si
pinfish, juvenile
Lagodon water,
rhomboides carrier
pinfish, juvenile
30 en SI.
Iagodon water, 12511
rhomboidal , carrier
ptntish, juvenile
30 en 54.
_______ water 12511
rhoaboides ,
pintiah, juvenile
U.)
—4 Lasodon water, 12511
rhomboide a carrier
pinfish, juvenile
Lagodon water 12511
rhomboides
pinfish, juvenile
Lagodon water 12511
rhomboides
pint lab, juvenile
Lagodon water 1260
rhomboides
pinfish
Lelostomus water, 12511
xanthurus carrier
spot, juvenile
11 Si.
gm.g 8 ( hiened) • DIO COFTB*TIO lID wav i OF m iuiRiiE ulIT UlII54JM 3
Dndttion s Uptake Elimination
Loca- Terminal
Ours— tion, Ours— conoen—
tion condi- Mean Range tion tration S S e—
( days) tiona Year Organ (ppm) (ppm) BCF Effects (days) (ppm) crease
2 16° C whole 0.98 1,000 no
26 ppt mortality
12 16—22° C 50%
20-32 ppt mortaL ity
5 lii 16—22° C whole 111 2,800 66%
20-32 ppt mortality
5 >111 lethal
5 35 22—32° C whole 109 21,800 IllS
114 _3 1 1 ppt mortality
10 2 16° C whole 38 380 no
26 ppt mortality
100 2 16° C whole 17 170 no
26 ppt mortality
100 no
mortality
1 56 23—32 C whole 27 27,000 1% 834 7.2 73
10—311 ppt mortality
Expgaure C
Isomer Concen—
or traticn
Aroclor (ppb )
12511 1
12511 5
Comeenta Ref.
26
14 14
I$l
1414
‘$11
26
26
26
Steady state 1111
-------
C
4
( I
r
a
0
0
4
Tim.i 8 ( tinusd ) • BIO U TR&TI0U I OF II !3TUUIIK 1 nhRT SSIIPl 3
Exposure Conditiona Uptake Elimination
Loca- Terminal
Isomer Concen— ira— tion, I ira— concan—
or tratian tion condi- Mean Range tion tration S Os—
Organism Source Aroclor (ppb) (days) tiona Year Organ (ppm) (ppm) BCF Effects (days) (ppm) crease Comments Ref.
Lelostomus water, 1254 I 56 23—32° C musols 6.5 6,500 811 2.0 69 Steady state 44
xanthurus carrier 10-311 ppt
spot, juvenile
I 1 SI.
Leioatoeus water, 1254 1 56 23—32° C liver 83 83,000 84 22 73 Steady state 114
xanthurus carrier 10-34 ppt
spot, juvenile
40mm SI.
Letostomus water, 1254 1 56 23—32° C gills 116 1 16,000 811 12 711 Steady state 1111
xanthurus carrier 10—311 ppt
spot, juvenile
4 SI.
Leiostosus water, 1254 1 56 23—32° C brain 8.3 8,300 811 2.9 65 Steady state 44
xanthurus carrier 10-34 ppt
spot, juvenile
4 SI.
Lelostomus water, 1254 1 56 23—32° C heart 13 13,000 811 2.5 81 Steady state 1111
xanthurua carrier 10—34 ppt
spot, juvenile
4 SI.
Leiostoaus water, 12511 1 33 • 14 I60 C whole 17 17,000 17% 1111
xanthurus carrier 16—32 ppt mortality
spot, juvenile
25mm Si.
Leioatcmus water, 12511 5 26 8—10° C whole 120 211,000 50% 114
xanthurus carrier 20-32 ppt mortality
spot, juvenile
2Ilsm Si.
Leiostomus water, 1254 5 38 28_330 C 50% lii i
xanthurus carrier 23—311 ppt mortality
spot, juvenile
7 1 1 m m Si.
-------
w
Year
7*31 .6 8 ( uzt.taued ) • BI0C0UC TR*TI0U AID TE ii r a IDTV*3II6 CWDARY I31IP S
E2’poaure C nditiona _________________________ ination
Loca— Terminal.
leomer Concen— Dura— Uon, Dura— concen—
or tration tion condi— tion traUon S De—
Aroclor (ppb) (daye) Uona BCF Effecta (days) (ppm) creaae
12511 5 115 28—33° C 30,1100 62%
23 3lI ppt mortality
Mean Range
Organ (ppm) (ppm)
whole 152
Organ lam
Letoatomue
zanthurus
epot, juvenile
7’lmo EL
Letoatomus
aanthurua
apot, juvenil•
Letoetomus
zanthurus
apot, juvenile
Letoatowue
zanthurua ,
spot
Plathichthye
fleaus
Baltic flounder,
adult-eggs
Source
water,
carrier
water
water
water
water
coaments Ref.
LA)
‘0
PCB
12511
5
20 1I5
lethal
26
125 1
5
>111
lethal
21
12511
1 I l 28
26
<0.111
Baltic
ovary 0.120
50 5
Sea
0.012,
lipid
reduction
in hatch
255 ppb.1I.6 ppb 1119
lipid, fish
w/120 ppb had
no tat
C,
p
r
S
a
0
0
4
-------
Exposure Conditions
ca-
Isomer Concen— 1 1ra— tion,
or tration tion condi—
Organism Source Aroclor (ppb) (days) Lions Year
Nereis virens water 12511 1.0
clam worm, adult
C3 sizes)
Homarus 12112
americanus 1251$
American
lobster, adult
Homarus 12112
americanua 12511
American
lobster, adult
Homarus 12112
americanua 1251$
American
lobster, adult
0
Hoaarus food TPCB 1 600 28—
anericanus >42
American
lobster, adult
Homarus food TPCB 1100 28—
americanus >42
American
lobater,adult
Iloaarus food TPCB 1100 112
americanus
American
lobst.r,adult
I • TPCB s t.traohlorobip$ enyl
TA .E 9. BI0 TIATI0U UD VECIS Or PC II NARIIR QDAkT IlSUN S
Uptake Elimination
Terminal
Ours— concen—
H.an Range tion tratton S 0.—
Organ (ppm) (ppm) BCF Eftects (days) (ppm) crease
whole 50—500 0
muscle 0.10 0.07—
0.13
hepato— 1.6 1.1—
pancreas 2.3
egg mesa 4.11 2.8—
6.0
hepato— 3.1 5.1 112 100
panoreae
hepato— 4.0 1.0 112 60
pancreas
tail 0.039 >0.01 42 80
steady atate
10—28% lipid
steady atate
10-28% lipid
steady state
not reached
0.1I 0.lIlI% lipid
Comeenta Ref .
80
I I
Frenchnana
Bay
Frenchaana
Bay
Vrenchmans
Bay
100 C
100 C
100 C
I ;
80
80
80
-------
Zeomer
or
Organie. Source Aroclar
Homaru . food TPCB
americanua
American
lob .ter,adult
Homarua food HPCB 1
americanu .
American
lobater,adult
Homarue food HPCB
americanua
American
lobeter,adult
I loearu . food HPCB
americanua
American
lob .ter,adult
Homaru . toad HPCB
americanua
American
lobater,adult
Homarue tntra- PPCH 2
americanua venoue
American 0.2 mg/kg
lobat.r,adult
Homaru . intra- PPCB
americanua venous
American 0.2 mg/kg
lob.ter,adult
1. HPCH s hexach lorobiphenyl
2. PPCS e pentachlorobiphenyl
hepato-
pancreas
Comeent .
eteady stat.
not reached
0.111 —0.72% lipid
steady state
10—28% lipid
steady state
not reached
10—28% lipid
steady state
not reached
0.11 O.11lI% lipid
steady state
not reached
0.1 1 1 0.72% lipid
cposure
Condition.
Loca—
Elimination
Terminal
Concen—
tration
(ppb)
Hora— tion,
tion condi—
(day.) tions
Tear
Mean
Organ (ppm)
Range
(ppm)
BCF
Effects
Dwa—
tion
(day.)
concen-
tration
(ppm)
S De—
creaae
hOD
112 10°C
claw 0.273
>0.07
82
80
550
4— 10°C
>112
hepato- 11.0
pancreas
7.3
112
100
1190
1 12 10°C
hep to— 111.2
pancreas
>2.9
112
1 10
1190
112 10°C
tail 0.027
>0.006
42
40
1190
112 10°C
claw 0.123
>0.011
42
Ref.
80
80
80
80
80
muscle
(7 50
45 50
-------
TABLE 9 (ContInued).
aim Ot Pc 11 IIIBIJE IDUY O)ISWIUS
.
I . ’)
Exposure
Conditions
Uptake
Elimination
Casmenta
Ret.
Organism
Isomer
or
Source Aroclor
Concen—
tration
(ppb)
I jra—
tion
(days)
Loca-
tion ,
condi—
tione Tear
Plean
Organ (ppm)
Range
(ppm)
BCF
Etfects
Dura—
tion
(days)
Terminal
concen—
tration
(ppm)
S De—
crease
Homarus
americanu
American
, adult
mire— ca
venous
0.2 mg/kg
—
egg
mass
39
50
11
Iltcrodadua
toncod
toacod, adult
1016
1254
Hudson River
Estuary 1978
Jan—Feb
whole 0.2
yb liver
& gonad
0.01—
0.7
lower cone. in
larger animals
65
Nicrodadus
tomeod
tomeod, adult
1016
1254
Hudson River
Estuary
1978
liver 37
11—
98
liver abnormality
NOT correlated
with PCB
65
Hicrodadus
tomeod
toacod, adult
1016
1254
Hudson River
Estuary
1987
gonad 1.2
0.01—
7.4
65
Kiorodadua
toncod
toodod, adult
1016
1242
Hudson River
Estuary 1978
whole 6.5
•
1211
.
Mlcrodadus
toiicod
toscod, adult
1016
1254
Hudson River
Estuary 1978
muscle 1.5
1211
I4icrodadus
tcacod
tomcod, adult
1254
Hudson River
Estuary 1978
whole 7.7
1211
Hicrodad ..z
icacod
tomood, adult
1254
Hudson River
Estuary 1978
usole 1.3
1211
-------
T* 2 9 ( atiinied). BI0a1UC TRAfl0U RID w z OP. m MIBUIE v*RT USUl S
Exposure
Conditions
Uptake
Elimination
Coeents
Ref.
Organism
Source
Isomer
or
Aroclor
Concen—
tratian
(ppb)
ra—
tion
(days)
Loca-
tion,
condi—
Uons
Year
Organ
) an
(ppm)
Range
(ppm)
BCF
Effects
Ours—
tion
(days)
Terminal
concen—
tration
(ppm)
S Pa—
crease
Gedus morhua
eod,adult
food
12511
1,000—
50,000
92
livers
3.5—
3.7 1 1
1116
Gadue morhu
cod,adult
food 12511
.
1,000—
50,000
92
teatee
0.05—
5.3
1116
fish
water
12518
61,000
77
fish
food
1—7
£
a
4
n
a
r
a
‘I
U
U
4
-------
aim v -i PcMe II MABE T lTIUT N JP
I1I.n4 . .. 4. .. .
TABLE 10.
p ur
UI1U1t.1Qfls
Loca—
Isomer Concen—
Dura— tion,
.
Terminal
or tration
tion condi—
Mean
Dura—
eoncen—
Organism
Source
Aroclor (ppb)
(days) tiona
Year
Organ
(ppm)
Range
(ppm)
BCF
Eftecte
tion
(days)
tration
S De—
Squalua
1242
Prenchman s
muscle
0.4
crease
Coenta
Ret.
acanthus
1254
Bay, ME
4
spiny dogfish,
adult
Squalua
1242
Frencheans
liver
1.9
canthua
1254
Bay, ME
4
spiny dogfish,
adult
Squalus
1242
Prenchmans
kidney
0.2
acanthus
1254
Bay, ME
4
spiny d’ rish,
adult
‘
Squalua
inira—
PPCB’
liver
acanthus
venous
7
11
4
spiny dogfish,
0.2
(*11)
adult
mg/kg
Squalue
intra—
PPCB
kidney
acanthus
venous
7
94
4
spiny dogfish,
0.2
adult
mg/kg
Squalus
intra—
FPCB
heart
acanthus
venous
7
99
4
spiny dogfieh,
0.2
adult
mg/kg
1 • PPCB =pentachlorobiphenyl
-------
LID P rn CF PC II LVIII PIDUBY C0U JNIDS
TLm.g ii.
.
Ui
Exposure
Conditions
Uptake
Loca-
Terminal
Isoser Concen—
I ra— tion,
Dura—
concen—
or tration
tion condi—
Mean
Range
tion
tration
S Do—
Organism
Source
Aroclor (ppb)
(days) tion.
Year
Organ
(ppm)
(ppm)
BCF
Errects (days)
(ppm)
crease
Comments
Ret.
eva_n
PCI
Denmark
1972
2.2
industrial area
156
ll ards
PCI lIx1O
49
low II
production
and hatchability
156
mallards
1254 single
dose
egg shell
thinning
short term
156
black duck
Northeast
USA and
Canada
1971
3.3
1—6.9
•
156
pheasants
1254 50 ng
192
low egg
production
end hatohability
156
ohiekem
Bay of
Fundy
1974
(0.010
156
chicken,
in—
1242
yolk
beak
156
egg—chick
jeoted
‘
abnormalities
ohicken, hens
food
1232 2x10
and
1254
,
teratogenic
156
ring doves
1254 i io
35
none
156
ring doves
1254
low hatching
rate in second
generation
2 generations
156
finches
PCI
Lab
liver
345
failure of
limb coordination
50% mortality
15
-------
Exposure
Conditions
Loca—
Uptake
Elimination
Isomer
Conoen—
I jra—
tion,
Terminal
or
tration
tion
condi—
Dura—
concen—
Organism
Source
Aroolor
(ppb)
(days)
tions Tear
Hean
Organ (ppm)
Range
(ppm) BCF
Effects
tion
(days)
tration
(ppm)
% De—
eider
PCR
Denmark 1970—
1972
35
14
crease
CQoments
Ref.
156
ducks,
PCB
Denmark 1974
adi— 2.2
purple
West Coast
156
sandptpers
of Greenland
woodcock
PCB
USA 1973
(11 state.)
wings 6.5
4.27 8.63
whole bird,
156
starling
PCR
Norway 1970
breast 0.014
gxtracted lipid
muscle
156
0
-------
Exposure
Conditions
Uptake
Elimination
Loca—
Terminal
Isomer Concen—
Ours— tion,
Ours—
concen—
or tration
tion oondi—
Ness
Range
tion
tration
S So—
organism
Source Aroolor (ppb)
(days) tions
Year
Organ (ppm)
(ppm)
BCF
Effects (days)
(ppm)
crease
Conments
Ref.
birds, adult
PCB
North
Atlantic
liver 24
fat, 535
liver 311
failure of
li.ib coordina—
tion, convulsions
wasted and
underweight
15
19 native
PCB
Germany
1974—
425
2.0—
156
bird speciea,egg
1976
547
terrestrial end
PCB
Spain
1974
5.6
5—
156
aquatic birds
6.2
carnivorous
PCB
Norway
1972
breaet 3.0
156
birds
suede
terrestrial
predatory birds
PCB
Denmark &
Greenland
1971
liver 137
1.3—
272
156
Bird feeding
PCB
Ragland
1978
liver 70
156
raptors
•
freshwater fish—
PCB
F ig1and
1968
liver 900
156
eating birds
•1
fish—eating
PCB
Upper Great
1973
339.7
156
birds, egg
Lake States
fish-eating
PCB
Louisiana
1973
35
156
birds, egg
Podiceps
PCB
Upper Great
1973
744.6
156
grisegna
Lake States
red-necked
greta egg
-------
Exposure
Conditions
Uptake
Elimination
Loca—
Terminal
Isomer Concen—
Dara— tion,
Dera—
concen—
or tration
tion condi—
Mean
Range
tion
tratton
S De—
Organism
Source Aroolor (ppb)
(days) tiona Tear
Organ (ppm)
(ppm)
BCF
Effects
(days)
(ppm)
crease
Conments
Ref.
pelicans
PCB
South 1973
Dakota
adipose
2.24
156
Pelecanus
PCB
USA 1971
6
(1.0—11
156
occidentalis
brown pelican,
egg
Pelecanus
PCB
South 1970
6.1
5—74.5
156
occidentalis
PCB
Carolina 1971
5.2
3.9—70.4
156
brown pelican,
PCB
1971
6.5
1.5-36.5
156
egg
PCD
1972
7.5
2.6—32.3
156
PCB
1973
4.7
0.9—19.3
156
Morus bassanus
PCB
England 1973
liver 7,1115
ll,720_
156
gannets
E. & W.
Coasts
9,570
.
Phalacrocorax
Canada, 1972
115.6
156
auritus
New
double-crested
Brunswick
comorant
Phalacrocorax
PCB
Canada 1972
breast 3.38
156
auritus
USA
muscle
double-created
.
c orant
cormorant.
PCB
Denmark 19711
Vest Coast
of Greenland
31.7
26.30
37.10
156
cormorant
PCB
The 1972
Netherlands
brain 190
liver 319
dead
156
cormorant
PCB
The 1973
Netherlands
carcasses 0.75
brain 0.69
0.50—1
dead
156
B
C
4
A
r
I ’
a
a
4
-------
T&ftE 13 (Ccntthued).
LID C PcBs LVI I I TIDYZIRY COUSIJMIDS
Mergus merganaer
cc on aergenaer
egg
Mergue
red crested
aerganser, egg
Ha liaectus
leucocophalus
bald eagle
HaUaectus
leucocephalus
bald eagle
Haliaectua
laucocephalus
bald eagle
Haliaectus
Isucocephalus
bald eagle, egg
Na liaectus
leucocephalus
bald eagle, egg
white—tailed
eagle, adult
white—tailed
eagle
Upper Great 1973
Lake States
Northeastern 1966—
USA and 1973
kftario
USA 1971
(17 States) 1971
1972
1972
USA 1972
‘ Kodiak,
Alaska
Adatral
Is le
Melne
Florida
Michigan
Minnesota
USA
carcasses 1115 .30—290
brain 75 .10—150
carcasses 600 .60—1200
brain 95 .65-190
brain 235
156
156
156
156
156
156
156
156
156
156
Exposure
Conditions
Uptake
Elimination
Loca-
Terminal
Isomer Concen—
Dura—
tion,
Ours—
concen—
or tration
tion
condi—
Mean
Range
tion
trstion
% Ge—
Organisa
Source
Aroclor (ppb)
FC D
(days)
tions
Upper Great
Lake States
Tear
1973
Organ
(ppm)
260.2
(ppm)
DCL
Effects
(days)
(ppm)
crease
53
Comments
Ref.
‘489.0
14314
PCD
PCB
LCD
PCB
PCB
LCD
LCD
PCB
LCD
LCD
156
1969
1970
1969
1969
1969
1969—70
1970
2.2
1.1
9.9
12.2
27.7
7.7
114,000
LCD
Germany 1972 52 6.1—97
156
-------
0
Exposure
Conditions
Uptake
Elimination
Cosmenta
Ret.
Organiam
Source
Isomer Concen—
or tration
Aroclor (ppb)
mra—
tion
(days)
Loon—
tion,
condi—
tions
Year
Organ
I1ean
(ppm)
Range
BCF
Effects
Dura—
tion
(days)
Tersinal
concen—
tratiofl S De—
(ppm) crease
IThite tailed
eagle, adult
PCB
Sweden
muscle
brain
215
29
190—240
I.’pulation on
decline
60
Pandion
haliactus
osprey
PCB
Finland
1972
25
156
Falco
peregrinus
peregrine falcon
PCB
USA
1970
2,000
156
Falco
peregrinus
peregrine falcon
USA
2,000
156
Falco
peregrthus
peregrine falcon,
young
Falco
colunbiarus
merlin, adult
PCB
PCB
.
Western
shore of
USA
Lake
Michigan
1970
1968—
1969
adipose
tissue
196
52.5
156
156
Falco
coluabtaris
merlin, imeature
PCB
Lake
Michigan
1968—
1969
28.6
156
Falco
sparveriua
sparrow hawk
PCB
The
Netherlands
1969—
1971
47
156
heron, adult
USA
900
156
-------
I -n
-
TA .E 13
CCo&4— —’)
. BIOU UC ThI?IO
kID
OF
PC Ill LVI II ! TIIRT IISUN S
Exposure
Conditions
Uptake
Elimination
Loca-
Terminal
Isomer
Concen—
1 ara—
ijon,
Dura— concen—
or
tration
tion
condi—
Mean Range
tion tration
S Do—
Organism
Source
Aroclor
(ppb)
(days)
tione
Tear
Organ (ppm) (ppm)
BC?
Effects
(days) (ppm)
crease
Comments
Ref.
gulls and skuas,
PCB
Scotland—
1972
muscle 535
156
large
Arctic
and liver
common gull
PCB
Norwgy
1971
0.11 trace—
0.8
156
gull
New
Brunswick
1972
7.11
156
gull, egg
PCB
France
1973
0.8
156
herring gull
PCB
Norway
1971
19.1 0.2—38
156
herring gull
Bay of
Fundy
1972
0.1
156
herring gulls
PCB
Bay of
Fundy
1972
adipose 1.1$
156
herring gull,
PCB
Upper Great
1973
2,221$
156
egg
Lake States
herring gull,
PCB
,.
USA
1973
300
156
egg
‘
terse
PCB
Long
Island
Sound
1971
Breaet 90 5—175
muscle
156
-------
ThEL 13 (ContInued) • 8IO I TR*TI AND VEC OF FCRa II AVIAN TNDTIIRY CORSENSES
141 1.
‘U
Exposure
Conditions
..__..
Loca-
Terminal
Isomer Concen—
ara— tion,
.
Ours—
concen—
or tration
tion condi—
Mean
Range
tion
tration
% De—
Organism
Source
£roclor (ppb)
(days) tiona Year
Organ (ppm)
(ppm) BCF
Effects
(days)
(ppis)
crease
Comments
Ref.
tarns, young
PCB
Great Gull 1969—
Island 1970
breast 25
muscle
156
Uriasalge
PCD
Oregon 1969
brain 11,000
dead birds
156
common murre
Coast
Uris aalge
PCB
Farallon 1971
lipids 168
156
common murre,
egg
Is land
Ceonhus grille
PCB
&igland, 1973
carcasses 3
dead
156
guillemot
Irtsb Sea 1973
1973
liver 50
carcasses 1.0
liver 0.53
shot
156
.
Ceonhus grille
FCD
Sweden, 1969
16
156
guillemot
Ealtia
Cepphus grille
PCB
Denmark, 197 1e
11.1
10.10—12.9
156
guillemot
West Coast
of Greenland
Cepphus grille
PCD
Raltic
tat 250
1 1I0_360
60
guillemot, egg
Sea
Cep hus grille
PCB
Sweden
16
7.9—21
60
guilemot, egg
Eagle owls
PCB
Sweden 1973
SE Coast 1973
brain 260
breast 110
muscle
Found dead
156
-------
Exposure Conditiona
Loca—
Isomer Concen— ira— tion,
or tration tion condi—
Source Aroclor (ppb) (days) tions
Sweden
Germany
tABLE 111 • BZ&a mATIOI AID m.im OF PCMe TIDUSThIIL PRUIARY WJI JMIDS
Uptake Elimination
Terminal
I)ura— concen—
Mean Range tion tration % Os-
Organ (ppm) (ppm) SCF Effects (days) (ppm) crease
Year
1973
0.1
156
19711 adipose 0.22
20 out of 22
sample.
156
Organism
herbivorous
mammals
harea
rabbit
12511
0.0125
28
abortions,
fetotoxicity
156
cows, nursing
cows, newborn
cows, 2 months
cows, 2 months
USA
USA
USA
USA
1977
1977
1977
1977
adipose
adipose
plasma
5.8
5.5
33
3. 11
156
156
156
156
I -n
LU
Comments Ref.
-------
TIELE 15. BI0 NC TRLTI LID T im 07 POSe II TEREIDTRILL LID TIDTILRT SJX IS
Exposure
Organism
Source
Isomer Concen—
or tratian
Aroclor (ppb)
Conditions
Loca-
I jra — tion,
tion condi—
(days) tions
Year
Organ
Mean
(ppm)
Range
(ppm)
ICY
Elimination
Terminal
Dura— concen—
tion tration
Effects
S Be—
mink
food
1254 5,000
(days) (ppm)
reproductive
failure
crease
Comments
Ref.
156
minks (found
dead)
PCI
New
England
1977
79 z amount
detected in minks
156
American mink
PCI
Sweden
1973
muscle
adipose
0.58
45
19711
156
fox
PCB
Cerasny
19711
adipose
2.5
1 out of 5
aagples
156
seal 1 adult
seal, pup
seal, adult
Pea
PCI
PCI
Baltic
Sea
fat
fat
milk
310
65
30
60
60
sea lion
PCI
South
California
high rate of
premature births
naturally
156
monkeys
12118 2,500
‘
lower fertility
lower birth
exposed
156
macmon mulatto
monkey
12118 1x10 5 —
3x1 0 5
.002.
hair loss
facial edema
156
macacm mulatta
monkey
12118 2.5x10 3
facial edema acne -
developed 1—2 sos
lesions severe
in females,
156
rhesus monkey
12118 3x 10 5
t r of stomach
moderate in males
rhesus monkey
1248 2.5 10
lining
156
-------
fiLl 15
( t4m..d) •
BIOj?—--ImATI LID
0? PC II TUBISTRIAL TUflLRY
Q 3JNUS
Exposure
Conditione
Uptake
Elimination
Loon—
Terminal
Isomer Concen—
Pure— tion,
Dir,— concen—
or tration
tion condi—
Ilean Range
tion tration
S De—
Organism
Source
Lroalor (ppb)
(days) tions
Year
Organ
(ppm) (ppm)
BC?
Effects (days) (ppm)
crease
Comeenta
Ref.
rhesus monkey
C30 1 11,000
28
central nervous
syetse degeneration
156
rhesus monkey
C30
degenerative
changes in liver
dose dependent
156
rhesus monkey,
C30
degenerative
slight to
156
lactating
changes in liver
of intent
moderate
1. C30 • Colphen & 30
U i
-------
summarize data in the literature relating to the bioacoumulation
and effects of PCBs. The data in these tables are arranged by
habitat and trophic level.
Biodegradation
Many factors affect the rate and extent of biodegradation
of PCBs in the environment, including the percent chlorine
composition of the isomers and Aroclor blends; the concentration
of the compound; temperature; moisture; indigenous microbial
population; aerobic or anaerobic conditions; presence of other
carbon sources; and other factors, many of which are not well
understood. PCB5 are fairly resistant to biodegradation,
however, isomers with fewer than four chlorine atoms per ring do
degrade in a variety of environmental media (Callahan et al.,
1979 , Smith et al. 19——).
Biodegradation of the lower—chlorinated isomers occurred
in activated sludge (e.g., metabolism by bacteria),with 81
percent degradation of Aroclor 1221 in ‘18 hours, (Griffin and
Chlan, 1980) and with mixed cultures of soil microbes.
Generally, bacteria are not able to metabolize PCB compounds with
more than three chlorine atoms per ring. Higher organisms are
more able to metabolize the higher—chlorinated PCB compounds.
(Nlsbet, 1976). Aquatic invertebrates can slowly metabolize
tetrachlorobiphenyls (four ohiorines per ring) and
pentachiorobiphenyls (five chiorines per ring). Birds and
mammals metabolize these compounds more rea .y, but have
difficulty with hexachlorobiphenyls (six chiorines per ring) and
56
M(TCALF a EDDY
-------
more highly—chlorinated PCBs. Jensen and Sundstrom (1974) showed
that PCB Isomers with 3 or 11 chlorine atoms (as are found in
Aroclors 12511 and 1260) are more easily metabolized by humans
than those with only one or two chlorine atoms (as predominate in
Aroclors 1016 and 1242). Although most PCB biodegradation
processes result in the formation of hydroxy—chiorobiphenyls,
there is evidence for the formation of chlorinated dibenzofurans
in chickens and rats (Nisbet, 1976). Thus, the biodegradation of
PCBs does not necessarily represent detoxification of the
compounds.
Bioconcentratlon
Biotic flux, i.e. the transport out of environmental
compartments via uptake by organisms, can be a substantial mass
transfer pathway for PCBs (Nisbit and Sarofim, 1972). As
hydrophobic, lipophilic compounds, PCBs are readily taken up by
blota. This bioooncentration is a function of the ambient
concentration of PCBs, the organisms under consideration, their
age, size, and other factors. It has been recognized, for
instance, that the higher chlorinated PCB blends are
bloconcentrated to a greater extent than are the lower
chlorinated blends (Callahan et al., 1979). The preferential
storage of higher—chlorinated PCBs can result in a higher average
chlorine composition in the PCBs stored than were present in the
original mixture. -
In the estuarine environment, PCBs can enter the food
chain in either particulate or soluble form (Mitchell, 19711).
57
-------
They adsorb readily to organic detritus, clay, and phytoplankton
(Harding and Phillips, 1978), and enter higher trophic levels
through the ingestion of food, sediment and water, with
subsequent absorption in the gut; absorption through respiratory
surfaces; or adsorption to the body wall or exoskeleton (Swartz
and Lee, 1980).
Both sediments and ambient water have been shown to
contribute to the bloaccuinulation of PCBs. Kiel et al. (1971)
reported Aroclor 12Z2 concentrations in the marine diatom
Cylindrica closterium 1100 times that of the ambient water.
Similarly, Fowler et al. (1978) reported PCB bioconcentration
factors in Nereis diversicolor , an annelid worm, of 800 in water
and 3.5 in sediment. A similar range of bioconcentration
factors is reported in Tables 2 through 15. The laboratory
determination of the bioaccunulation potential of PCBs, which was
used in the establishment of EPA criteria, was shown to be around
2711,000 times the PCB level in the test water (Nisbet, 1976).
Based on the relative concentrations in the water and sediments,
Fowler et al. determined that 85 percent of the PCB body burden
in N. diversicolor could be accounted for by direct uptake from
the sediment, due to the relative concentration of PCBs there.
Indications in that study were that the particulate fraction of
the sediments had higher bioavailability than the interstitial
water.
PCBs are strong.y lipophilic (lipid loving), and thus one
of the most significant factors affecting their accumulation and
58
-------
partitioning in biota is the lipid content (fatty substances) of
individual organisms. For both carp and channel catfish, Hunter
et al. (1980) reported a positive correlation between the amount
of lipid in fish fillets and the concentration of PCB5. Thomann
et al. (1980) reported that PCB concentrations in striped bass
were not significantly correlated with lipid content, however,
such a correlation was found in trout, salmon and carp data cited
by Thomann and St. John (1979). Graham (1976) found that the
mean PCB level in fish oil was 32 times that of fish meal from
which most of the oil had been extracted.
Due to variations in the lipid content of different
tissues, and other metabolic differences, the bioaccunulation of
PCBs can also vary within an individual organism. The data of
MoLeese et al. (1980) revealed that the hepatopancreas (tonalley)
of lobsters had significantly higher PCB concentrations than
either the tail or claw, with the tail having the lowest
concentrations. Similar studies of lobsters dosed with PCBs
revealed concentrations of Aroolors 12142 and 12514 in the
hepatopancreas to be 15 times higher than those in the muscle,
and concentrations in the eggmass 1.8 times higher than that of
the hepatopanoreas (Bend et al., 1976). Hansen et al. (1971)
reported that concentrations of Aroclor 1254 in spot, an
estuarine demersal fish, were highest in the liver, followed by
the gills, the whole fish, the heart, the brain, and the
muscle. Additionally, Klauda et al. (1981) noted PCB
59
-------
concentrations in the liver of tomcod 30 times higher than in the
gonad, and 1814 times higher than in the remainder of the
organism.
Rapid decreases in PCB concentration during spawning were
observed in quahogs (Deubert et al., 1981) and oysters (Parrish,
19714; Wilson and Forester, 1978), indicating that PCBs may be
stored in the gonadal tissue of these shellfish, and eliminated
in the gametes. Thus, the sex and reproductive state of an
organism may influence the bioscoumulation rate, due to metabolic
changes in lipid deposition (e.g. with many species, females tend
to be larger and have a higher lipid content than males).
Variation in rates of PCB bloaccumulation among individual
organisms of the same species may also be attributed to the sex,
size, and age of the organisms. For both plankton and fish,
increasing organism size appears to relate to increasing
concentration. Older fish may retain higher body burdens of PCB,
due to reduced excretion rates (Thomann and St. John, 1979).
Fish experiencing highly variable temperatures and faster growth
rates have been found to accumulate PCBs at a faster initial
rate, and to achieve significantly higher concentrations at high
body weights (Spigarelli et al., 1983). The effect of
temperature fluctuations is attributed to associated increases in
feeding, growth, and lipid deposition, which thereby enhance the
uptake of lipophilic compounds.
The reproductive state, size, and age of an organism may
also be related to changes in habitat, which in turn can affect
60
-------
PCB uptake. The American eel for example, is a catadromous fish
which spawns in the Sargasso Sea, but spends most of its life in
coastal estuaries and freshwater streams. The females move
further inland than the males. Generally, eels seek a muddy
bottom habitat and lie buried in the mud during the daytime, and
most of the winter (Bigelow and Schroeder, 1953). Consequently,
eels are most likely to accumulate substances like PCBs during
the portion of their life cycle which brings them closest to
sources of contamination. Their extensive contact with bottom
sediments and absence of large surface scales, as well as their
high lipid content, make them particularly susceptible to PCB
accumulation. Fisheries data collected by Graham (1976) supports
this conclusion. In a survey of PCB levels in commercial marine
fish harvested in Canada, Graham found average concentrations of
0.56 ppm PCB in eels caught in marine waters and 7.27 ppm in eels
caught in the St. Lawrence River. Eels from the St. Lawrence
were higher in PCB concentration than any other commercial
species. Of the freshwater eels, the smallest individuals
averaged 2.95 ppm PCB, and the largest averaged 12.37 ppm. This
distinction may have been related to body size alone, or to
sexual differences, since females are generally larger than
males.
Bioaccumulation of PCBs can reach an equilibrium, with the
steady state concentration varying according to the species, the
tissue, and the PCB source and concentration. Sanders and
Chandler (1972) observed a time of 7 days to a steady state
61
-------
concentration In mosquito larvae, and more than 21 days in glass
shrimp. Striped bass larvae reached steady state In k8 hours,
with 80 percent of the final concentration accumulated during the
first 12 hours (Califano et al., 1980). This relatively short
time to equilibrium may have been due to PCBs becoming limited in
the system, as the larvae had already accumulated 60 percent of
the available PCB. Spot took k2 days to reach an equilibrium
concentration (Hansen et al., 197k). In all of the above
studies, the source of the PCBs was ambient water containing
between 1 and 1.5 ppb Aroclor 125k. Time to equilibrium Is
quicker in Ingestion of water than by other sources. When the
time to equilibrium Is longer, an organisms physiological state
may change such that a true equilibrium Is never reached (Nisbet,
1976).
As with the actual bl000ncentration factors, different
tissues within an organism exhibit different equilibrium
dynamics. In a study of lobsters fed mussels containing two of
the PCB isomers, tetrachioroblphenyl and hexachiorobiphenyl,
concentrations of both Isomers in the lobster hepatopancreas
reached a steady state in 28 days, but the tail and claw tissue
levels were still increasing after k2 days (McLeese et al.,
1980).
Similar trends in the rate of depuration after removal of
the PCB source seems to indicate a reversible metabolic
process. In the lobster study described above, 80 percent of the
tetrachloroblphenyl was purged from the tail and claw tissue in 6
62
-------
weeks, at which time cocicentrations in the hepatopancreas had
decreased by only 60 percent. Results were similar for
hexachiorobiphenyl, with a 90 percent decrease in the claw and 110
percent decrease in both the tail and the hepatopancreas (MeLeese
et al., 1980). Bend et al. (1976) also reported that the muscle
tissue of lobsters depurated much more quickly than either the
hepatopancreas or egg masses.
Depuration studies of oysters showed a decrease in PCB
concentration to a steady state level, which was possibly
sustained by the resuspension of contaminated sediments (Wilson
and Forester, 1978). Califano et al. (1980), demonstrated that
larval striped bass placed in clean seawater for 118 hours
eliminated 18 percent of the total PCBs they had accumulated.
The rate of elimination was reportedly fastest during the second
211 hours.
Trophic Transfer
The bioconcentration of PCBs in a sector of the food web
is affected not only by the ambient environment and organisma].
morphology/physiology, but also by the food sources of the
organisms. Accumulated PCBs are readily transferred from prey to
predator. In a study of PCB bioconcentration in brown trout,
Spigarelli et al. (1983) determined that less than 5 percent of
the total accumulated PCBs were derived from ambient water, with
the remainder coming from the food source, in this case, alewife.
As PCBs are transferred to successive trophic levels,
their concentrations can be magnified. Thomann et al. (1980)
63
-------
reported a 10 fold increase in estuarine food chain PCB concen-
tration from phytoplankton to striped bass in the Hudson River
Estuary. Trophic transfer of PCBs does not, however, always
result in the magnification of PCB concentration, due to
variations in diet.
The diet of an organism is obviously not independent of
its habitat. In an estuary, for example, bottom dwelling primary
consumers feed on microorganisms, benthic invertebrates, organic
detritus and plant material, all of which can accumulate PCBs
from contaminated sediments. In an Oklahoma stream where the
sediments were heavily laden with PCBs, Hunter et al. (1980)
determined that the concentration of PCBs in detritovores (carp)
was significantly greater than In either omnivores (catfish) or
carnivores (bass and crappie). However, other factors may have a
stronger influence on PCB accumulation than does the diet.
Graham (1976) found that, of the commercial marine fish caught In
Canada, demersal (bottom dwelling) species generally had a lower
PCB body burden than did pelagic (open water) species. One
explanation for this might be a higher average lipid content and
body size in the pelagic species. Bluefin tuna, a high trophic
level consumer and probably the largest of the commercial
species, had average PCB concentrations of 2.6 ppm, more than 6
times that of other pelagic fish (0.1$ ppm), and 25 times the
average concentration of the deinersal fish.
6 1 $
-------
41ra t ion
The migration of organisms, e.g. the seasonal movement of
birds or the passage of eel larvae from the ocean to inland
streams, necessarily results in the migration of any toxic
substances which they have bioaccumulated. Thus, the fate of
PCBs in the environment can be far more complex and far—reaching
than can be described by physical transport processes alone. In
the Hudson River Estuary, for example, a wide range in PCB
concentrations in striped bass is attributable to the seasonal
migration characteristics of these anadromous fish (Thomann and
St. John, 1979). Concentrations in eels will also vary
significantly with their migratory patterns. Fall sampling of
eels from an estuary, for example, might reveal significantly
higher PCB concentrations than would sampling in the spring,
since the fall catch would include large females returning to the
sea from inland waters, and the spring catch would consist
primarily of resident males and young females in the process of
moving landward. Consequently, migration can have a significant
effect on both the flux of PCBs In the environment, and the
variation in concentration of PCBs in the biological community of
any given locale.
65
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Toxicological Effects of PCBs
The toxicity of PCBs is highly variable, both in magnitude
and in effects (Tables 2 through 15). In some situations, PCBs
can be lethal and in others, sublethal, but causing some physical
disorder. For example, PCBs in various concentrations have been
shown to be lethal to phytoplankton (Moore and Harrlss, 1972);
diatoms (Biggs et al., 1980; Fisher, 1975); shrimp (Nimmo et al.,
197k; Duke et al., 1970); shellfish (Duke, 1974) and finfish
(Hansen et al., 1971, 1976; Nebeker et al., 19711; Defoe et al.,
1977; Johansson et al., 1970; Jensen, 1970; Duke, 19711; Schimmel
et al, 19711).
At sublethal levels, PCBs have been reported to cause
lesions in the gills and liver of fish (Walker, 1976; Duke,
1974); increased thyroid activity in coho salmon (Walker, 1976);
beak abnormalities (Wassermann et al., 1979) and general limb
weakness (Bagen and Bourne, 1972) in birds; hair loss, acne, and
degenerative changes in the liver and central nervous system of
monkeys (Wassermann et al, 1979); and skin lesions (Schwartz and
Peck, 19113) and increased liver enzyme activity (Risebrough,
1969) in humans.
PCBs can also result in behavioral aberrations and effects
which alter community structure. These compounds have been
implicated as a cause of reproductive failure and deficiencies in
1
Daphnia (Nebeker and Puglis;, 19711); fathead minnows and lagfish
(Nebeker et al, 19711); Atlantic salmon (Hogan and Brauhn, 1972;
66
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Johansson et al, 1970; Jenson, 1970); and birds, mink and sea
lions (Wassermann et al., 1979). Relatively low levels of PCB
have been reported to inhibit the growth, photosynthetic activity
and productivity of phytoplankton (Biggs et al., 1980) and
diatoms (Moore and Harriss, 1972; O’Connors et al., 1978; Mosser
et al., 1977; Fisher, 1975), and the growth of lake trout
(Walker, 1976). Particularly in complex ecosystems, e.g.
estuaries, any such Impacts on the lowest tropic levels can
profoundly affect the entire ecosystem.
PCBs exhibit selective toxicity, whereby different
biological species vary in their sensitivity to the chemical
compounds. For example, 100 ppb of Aroclor 1251$, with 148 hours
exposure time was reported to have no effect on juvenile pinfish,
but was 100 percent lethal to pink shrimp (Duke, 19714).
Sheepshead minnow fry are considered to be the most sensitive
estuarine organism, with 50 percent mortality at 0.1 ppb Aroclor
1251$ and 100 percent mortality at 3 ppm, a level at which adults
were unaffected after 14 weeks (Duke, 19714; Schimmel et al.,
19714). This selective toxicity can significantly affect the
community structure in an ecosystem. PCB concentrations of 5 to
10 ppb, for example, have been found to inhibit the growth,
photosynthesis and productivity of Chiorella , altering its
species composition and size (Biggs et a]., 1980), while a
concentration of 1000 ppb did not inhibit the gi .dch of another
green flagellate, Dunnaliella tertiolecta . Concentrations up to
10 ppb PCB even Increased the competitive success of this
organism (Mosser et a]; 1977).
67
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Of the many PCB compounds, the formulations with 3 to 5
chlorine atoms per biphenyl, as predominate in Aroclors 12112 and
12118, appear to be the most toxic to fish (Walker, 1976). This
suggestion is substantiated by Nimmo et al. (19711), who reported
that the LC 50 (concentration resulting in 50 percent mortality)
with adult scud was 21100 ppb Aroclor 12511 and only 52 ppb Aroclor
12118. Nebeker et al. (19711), however, found that the MATC
(maximum acceptable toxicant concentration, e.g. the threshold
concentration at which the substance begins to have toxic effects
on a given organism) for fathead minnow was lower with Aroclor
12511 than with Aroolor 12112. Duke (19711) found that with both
oysters and pink shrimp, Aroclor 12511 was more toxic than Aroclor
1016, yet the latter is one of the lesser chlorinated blends,
with an average of 111 percent chlorine.
One factor which may influence the relative toxicity of
different PCB compounds is the duration of time for which
organisms are exposed to them. For example, juvenile pinfish
exposed to 100 ppb Aroclor 12511 for 2 days suffered no mortality,
yet there was more than 50 percent mortality after 12 days
(Hansen et al., 1971). Stalling and Mayer (1972) reported that
the oral toxicity of Aroclors 12112 and 12118, as well as 1251$, to
cutthroat trout increased greatly over long exposure periods, and
also with increased temperature. Similar results have occurred
with channel catfish and rainbow trout (Hansen et al., 1971), and
with pink shrimp (Duke, 1971$). In all likelihood, this chronic
toxicity is the result of PCB bioconcentration to levels well
68
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above that of the ambient environment, and beyond the threshold
of toxicity.
From a review of selected literature, it is obvious that
the chemical, physical and biological characteristics of PCBs
affect their transport, fate and effects in the environment.
This general review serves as the foundation for interpretation
and comparison of the Acushriet Estuary PCB data base; for
identification of critical data deficiencies; and development of
resource management decisions related to effective remedial
action.
69
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SECTION 2
-------
SECTION 2
ASSESSMENT OF THE ACUSHNET ESTUARY
PCB DATA BASE
Data Management
General
The Acushnet Estuary PCB data base presently contains more
than 5,000 indivIdual data entries, representing approximately
3,700 PCB analyses and i,I 0O analyses of other parameters,
primarily heavy metals. It reflects the efforts of 21 data
collecting agencies and 23 analytical labs over the past ten
years. Almost all of the data contained in the file are from the
Acushnet Estuary, surrounding land, and adjacent Buzzards Bay.
Each data entry includes the following information, where
relevant and available:
• Sample identification (sample, station and lab
numbers).
• The agency which performed the study.
• Sample type, in several levels of detail.
• Location of sampling Cx, y coordinates) and date and
time of sample collection.
• The lab which performed the analysis, the date of
analysis, and the analytical methods used.
The parameter analyzed, measured concentration, units
of’ measurement, detection limit, and solids content of
the sample.
• Any additional information and comments.
70
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Data Evaluation
In order to ensure the quality of the data base, all of
the data were screened using criteria developed to evaluate the
reliability of each measurement. Based on this evaluation, the
data were divided into three categories: “reliable” data, or
those for which the sample collection and analytical methods were
documented and possess a reliability worthy of the fullest
confidence; “incomplete” data, for which the documentation
necessary to ascertain the reliability was unobtainable; and
“unusable” data, which possessed collection and/or analytical
deficiencies which precluded their use.
Figure 2 illustrates the procedure used in evaluating the
data. In cases where quality control documentation was not
available to substantiate the analyses, the data was designated
“reliable” only if the laboratory performing the analysis
maintained State certification for the analysis of pesticides,
herbicides and volatile organics (under Section 3OZ (s) of the
Federal Water Pollution Control Act), thus proven procedures (1 O
CFR Part 136) were used. This certification, coordinated through
the Quality Assurance Branch of the U.S. Environmental Protection
Agency’s regional offices, includes the comparative analysis of
split samples by participating laboratories.
On the basis of this data evaluation, 91 percent of the
data base was deemed reliable, 5 percent incomplete, and 14
percent unusable. All subsequent references in this report to
the PCB data, unless otherwise indicated, are based only on the
“reliable” data base.
71
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DOCUMENTATION
NO
YES INDICATES ______
ACCEPTABLE
METHODOLOGY
QUALITY
YES
_______ CONTROL _______
NOT SUFFICIENT
I DOCUMENTATI}__ 1 DOCUMENTATION
TO DETERMINE
I AVAILABLE
SUBSTANIATION —
YES STATE OR EPA NO
OF RESULTS BY _______
CERTIFIED
OUALITY CONTROL
LABORATORY
MEASURES
R RELIABLE
I INCOWLETE
U UNUSABLE
FIGURE 2. USE OF DATA EVALUATION CRITERIA
MEtCALF & EDDY
-------
Objectives
Once the reliability of the data base was established, its
actual utility was examined relative to its contributing
essential information regarding:
• The location and severity of contamination in the
Acushnet Estuary area.
The specific contaminants present.
The critical pathways (physical, chemical and biologi-
cal) and fate processes acting in the transport and
partitioning of contaminants in the estuary.
The implications of contamination, including public
health hazards, the health of the ecosystem, and
economic impacts.
The effectiveness and impacts of potential cleanup
alternatives.
The following discussion summarizes and assesses the
existing reliable data relating to these issues in the Acushnet
Estuary; describes the approaches used in making the assessment;
and Identifies apparent data gaps as well as critical areas
requiring remedial action.
Data Base Assessment
Location and Severity of Contamination
Table 16 summarizes the major sample types included in the
data base. (A more detailed breakdown of sample types Is
73
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TABLE 16. SUMMARY OF “RELIABLE” DATA BASE
Number
Sample of Data
Type Entries
Air
Sediment 2729
Waste 199
Water 223
Lobster 31 16
Blue Mussel 90
Quahog 5110
Winter Flounder 56
Misc. Shellfish
(6 Species) 23
Misc. Finfish
(19 Species) 1140
Misc. Sample Types (6) 195
-------
contained In Appendix A). More than 50 percent of the nearly
,600 data entries represent analyses of estuarine sediments, and
11 percent are water column analyses from the estuary. An
additional 26 percent of’ the data are analyses of aquatic
biota. Thus, more than 75 percent of the existing data base
comprises samples from the Acushnet Estuary itself, as opposed to
land—based locations such as the disposal sites, industrial
plants, and municipal facilities. This fact in itself may
indicate a significant data gap, although the estuary is where
the most pervasive contamination has occurred.
The PCB data base file contains approximately 250 data
records from analyses of various wastes. Most of these data
represent wastewater, sediment, sludge, grit and ash samples from
the New Bedford sewer system and water and wastewater treatment
facilities, although there are also some data from the industrial
processes at Aerovox Incorporated and Cornell—Dubilier
Electronics. Of the sewer system data, the only measurable PCB
concentrations occurred at and below the Cornell—Dublier plant.
As recently as 1981, concentrations of 63 mg/i Aroclor 1016 were
measured in the sewer system by the Massachusetts DEQE. Within
the treatment facilities, PCBs are concentrated in the sludge to
levels as high as 190,000 ppm (dry wt) Aroclors 121 2/1251I.
Studies involving the monitoring of PCB levels in the
ambient air of the Acushnet Estuary area revealed concentrations
(in 139 records) ranging from nondetectable to 800 ng/m 3 Aroclors
1016/12’42. The highest concentrations were measured by EPA in
75
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1977 and 1978 at the two capacitor manufacturing plants In New
Bedford, Aerovox Incorporated and Cornell—Dubilier Electronics.
More recent sampling (in 1982) at these locations revealed
significantly lower concentrations, within a range of less than 1
to 100 ng/in 3 Aroclors 1016/12L 2 in the vicinity of Aerovox, and
less than 10 ng/m 3 near Cornell—Dubiller. This recent study (by
EPA) showed the highest ambient air concentrations (lkO ng/in 3
Aroolors 1016I12! 2) to occur at the former dump site on
Sullivan’s Ledge. Most of the New Bedford area air monitoring
has been conducted in areas of known or suspected PCB contamina-
tion. There are relatively few data records representing
“background” PCB levels in the air around New Bedford and
Fairhaven.
Tables 17 and 18 summarize PCB concentrations in estuarine
sediment and biota samples taken from the Acushnet Estuary
itself; in the Inner New Bedford Harbor (above the hurricane
barrier), and in the Outer Harbor (between the hurricane barrier
and Clark’s Point). Particularly In the Inner Harbor, the
Acushnet River Estuary is one of the most severely PCB
contaminated estuaries in the world.
For example, sediments in Raritan Bay, at the mouth of’ the
heavily PCB contaminated Hudson River between New York and New
Jersey, contained PCBs at concentrations of’ 0.003 to 2.0 ppm (dry
weight) (Stainken and Rollwagen, 1979). Bopp et al. (1981)
reported PCB levels in the lower Hudson River of 0.7 to 5.8 ppm
(dry weight). Sediment PCB concentrations further up the
76
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TABLE 17. PCB CONCENTRATIONS IN INNER HARBOR,
ACUSHNET ESTUARY
No. of
Records Minimum Maximum Median Mean
Sediments
( ppm dry wt. )
Aroclors 1221;
1232 58 ND ND ND ND
Aroclor 1016 110 ND 0.3 ND 0.1
Aroclor 12142 75 ND 730 ND 1.0
Aroclor 12148 85 ND 5100 29 333
Aroclor 125k 323 ND 66500 13 1221
Aroclor 1260 58 ND ND ND ND
Blot a
( ppm wet wt.)
Quahog
Aroclor 1221;
1232; 12 l2
Aroclor 1016
Aroclor 12148 —— ——
Aroclor 12514 3 0.1 1.6 0.5 0.8
Aroclor 1260
Eel
Aroclor 12514 l 4 11 730 2 140 2614
Winter Flounder
Aroclor 12511 5 6 22 11 11
Lobster
Aroclor 12112
Aroclor 12118
Aroclor 12514
Aroclor 1260
-------
TABLE 18. PCB CONCENTRATIONS IN OUTER HARBOR,
ACUSHNET ESTUARY
No. of
Records Minimum Maximum Median Mean
Sediments
( ppm dry wt. )
Aroclors 1221;
1232 1J 1 4 ND ND ND ND
Aroclor 1016 63 ND 25 ND 0.14
Aroclor 12142 614 ND 314 ND 2.0
Aroclor 12148 68 ND 98 1.0 6.0
Aroclor 12514 92 MD 102 6.1 12
Aroclor 1260 77 ND 50 ND 0.7
Biota
Iprm wet wt.
Quahog
Aroclors 1221;
1232; 12142 iLl ND ND ND ND
Aroclor 1016 111 ND ND ND ND
Arocior 12148 15 ND 6.0 0.3 0.9
Arocior 12514 30 ND 3.5 0.14 0.7
Arocior 1260 114 ND ND ND ND
Eel
Aroclor 12514 3 12 38 111 21
Winter Flounder
Aroclor 12514 15 0.2 8.3 2.5 3.0
Lobster
Aroclor 12142 14 ND ND ND ND
Aroclor 12148 5 2.0 21 8.7 11
Aroclor 12514 55 0.6 8 4 5.14 12
Aroclor 1260 14 1.0 3.1 1.7 2.0
-------
Hudson River, near PCB point sources, were often greater than 50
ppm, and seldom less than 25 ppm (Clesceri, 1980). In the
Escambia Ri’ er Estuary, Florida, sediment PCB concentrations of
500 ppm (dry weight) near the source outfalls have been reported
(Duke et a]., 1970). In the vicinity of several wastewater
treatment plant outfalls in the nearshore waters of San Diego,
California, bottom sediments had a median of 0.022 ppm (dry
weight) of PCB (Young and Hensen, 1977).
These New York, New Jersey and Florida estuarine locations
are referred to in the literature as being severely contaminated,
yet none of them have measured PCB concentrations approaching the
more than 10,000 ppm (dry weight) found in the upper portion of
the Acushnet Estuary. The median concentration of PCBs in the
New Bedford Inner Harbor, at 29 ppm (dry weight) Aroclor 12L 8, is
a full order of magnitude higher than in most of the other
estuarine locations studied. Only in the upstream reaches of the
Hudson River,New York and in the Escambia River Estuary, Florida
have such high concentrations been reported. Median concentra-
tions in the Outer Harbor area of the Acushnet Estuary are
comparable to concentrations in the Hudson River Estuary,
although the latter does not have measured concentrations nearly
as high as 100 ppm (dry weight).
There have been 138 water column analyses in the Acushnet
Estuary, all of which represent samples taken inside the
hurricane barrier. Although concentrations in the water column
79
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were to a large extent nondetectable (<0.5 ugh), levels as high
as 6.1 mg/i Aroclors 12148/12514 were measured.
PCB concentrafions in biological organisms inhabiting the
Acushnet Estuary are also indicative of contamination.
Particularly for the Inner Harbor, however, the data are limited
and therefore somewhat inconclusive. Of the organisms sampled,
eels had the highest concentrations, with a median of 2140 ppm
(wet weight) Aroclor 12514 in the Inner Harbor and 114 ppm Aroolor
12514 in the Outer Harbor. Concentrations in quahog and winter
flounder were also higher in the Inner Harbor than outside of the
hurricane barrier, at 0.5 and 11 ppm Aroelor 12514 respectively.
Lobsters sampled from the Outer Harbor were significantly
contaminated with PCB levels of 8.7 ppm Aroclor 12148, but there
are no lobster data for the Inner Harbor, where concentrations
could be expected to be higher. The levels of PCBs in the
Acushnet Estuary biota are generally much higher than those found
in Escambia Bay, Florida (Duke et al., 1970); Raritan Bay,
New York (Stainken and floliwagen, 1979); and Boston Harbor, Mass.
(Metcalf & Eddy, 1979).
In general, the range in PCB concentrations in the
Acushnet Estuary is exceptionally wide, with Aroelor 12514
analyses of Inner Harbor sediments ranging from nondetectable to
66,500 ppm (dry weight). This wide range in concentration may be
due to nonhomogeneity in the occurrence of PCBs in bottom
sediments, or to variability in the analyses. Variability in PCB
concentration in the biota is somewhat less than in the
80
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sediments. The Influence of a few very high concentrations on a
data set is evident in the mean concentrations listed in
Tables 17 and 18. Particularly in the sediments, the mean values
are well above the median concentrations measured. Statistical
analyses of the sediment data within 1 km 2 grid sections of the
estuary revealed standard deviations greater than or equal to the
mean. This distribution makes it very difficult to actually
quantify the volume of PCBs in the estuary, or to comprehend the
severity of contamination in any one area.
A more suitable way to analyze this contaminant
distribution is with a spatial representation, which relates a
measured concentration to its location in the environment.
Spatial representation is particularly appropriate for the
estuarine data, as opposed to air data, because it varies
spatially with changing climatic conditions, and data from the
sewerage system, which is essentially linear, according to the
system layout. Data from upland disposal sites, such as the
landfill, Sullivan’s Ledge, and the additional unidentified sites
referred to in the RAMP (Weston Associates, 1983), would also
best be analyzed in a spatial sense (on an x—y plane as well as
over depth), however the location of sampling of these sites, for
the limited data in the existing data base, does not contain the
information and precision necessary for such an approach.
Although contamination does occur at these upland sites, the
actual distribution of PCBs within the landfill and Sullivans’
Ledge remain essentially undefined and merits more detailed
81
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sampling. The focus of the remainder of this discussion is on
the location of contamination within the Acushnet Estuary as
defined by PCB concentrations in the e. tuarine sediments.
Utilizing a purely statistical approach, a linear
regression analysis was performed on the estuarine sediment data
to determine whether there was any correlation between PCB
concentration and location along the length, or y axis, of the
estuary. Both Aroclor 12 8 and Aroclor 1251 concentrations
exhibited a statistically significant (p < 0.01) positive
correlation with north/south position in the Acushriet River
Estuary, north of the hurricane barrier. Sediment concentrations
are highest at the top (north end) of the estuary, decreasing
further south towards the mouth of the harbor. Concentrations of
Aroolors 1016 and 12L 2 were not significantly correlated with
north/south position. There was no significant correlation shown
for concentrations of any of the Aroclors between the hurricane
barrier and the Clark’s Point/Wilbur Point transect, although
there was (with Aroclors 12Z 8 and 125’s) for the entire length of
the estuary, from Clark’s Point to just north of Aerovox. This
may be due either to the Influence of the treatment plant
outfalls at Clark’s Point, the widening of the estuary south of
the hurricane barrier (probably resulting in more east/west
transport), or the relative sparseness of data in the southern
portion of the estuary. In order to better illustrate these
trends, and to permit the interpretation of large amounts of
82
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data, a graphical approach to the data presentation was
undertaken.
Preliminary delineation of the locations of sample
collection and the distribution of contamination within the
Acushnet Estuary utilized a vector based computer graphics system
linked to the data base management system. Specific data sets,
e.g., surface sediments, were selected, and their sample
locations (listed as x,y coordinates in the USGS Transverse
Mercator Grid System) were plotted on a digitized map of the
estuary. Figure 3 is a sample of this mapping approach, showing
sampling locations of shallow (1 to 8 cm deep) sediments in the
estuary. Similar maps were generated for surface sediments (0 to
14 cm) and deep sediments (> 8 cm).
A second set of preliminary maps, depicting the PCB
concentrations (within range intervals) associated with each
sampling site, was developed for inclusion in the RAMP document
(Weston AssocIates, 1983). Figure 1 is an example from this map
set. It should be noted that both of these sets of preliminary
maps were developed prior to completion of the data evaluation.
They represent all of the data collected since 1977, not the
entire data base. The basic mapping approach used here
integrated the information pertaining to the location of PCB
sampling with that relating the PCB concentrations measured. As
Figure 11 illustrates, however, the large amount of’ data collected
within relatively small areas of’ the estuary make the map
somewhat “busy”, and difficult to interpret. In order to provide
83
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ESTIJARINE SEDIMENT DATA
SOURCE: EPA REGION I ACUSHNET ESTUARY
PCB DATA MANAGEMENT SYSTEM
30 NOVEMBER, 1982
NEW BEDFORD
N
CO.Dli’.\
FIG. 3 SAMPLING LOCATIONS - ESTUARINE SHALLOW SEDIMENT DATA
FAIRHAVEN
/
EDDY
-------
ESTUARINE SEDIMENT DATA
MAP SYMBOL
1
2
3
4
5
6
7
8
LEGEND
CONCENTRATION RANGE
(PPM DRY WT)
<1
1—10
10—50
50—100
100—500
500—1000
1000—10,000
>10 ,000
SOURCE: EPA REGION I ACUSHNET ESTUARY
PCB DATA MANAGE1 NT SYSTEM
30 NOVEMBER, 1982
NEW BEDFORD
2
2
3
FAIRHAVEN
‘K
-a
1 .
2 Li
FIG. 4 ES’rUARINE SEDIMENT DATA - AROCLOR 1254
AEROVOX
‘I
3
41
;
2
3
: 5
2
I
3
2
CO. DU.
,1
2
2
I)
MFTCALF & EDDY
-------
a more easily readable, yet Informative picture of the PCB
distribution in the Acushnet Estuary, a similar approach was
employed using color rastar graphics.
In this approach, sampling points were color coded
according to the measured PCB concentration, in half—step log
intervals. Ten colors were used to represent a range in
concentration from less than 1 ppm (blue) to greater than 10,000
ppm (red) (Figure 5). These maps, the upper portions of which
are presented in Figures 6 through 13, were prepared for each of’
four data sets: Aroclor 121 8 in surface sediments; Aroclor 125!I
in surface sediments; Aroclor in 1251 shallow sediments; and
Aroclor 125L1 in deep sediments, all derived from the entire
reliable data base.
These color coded point maps are highly informative
regarding both the distribution of PCB contamination throughout
the estuary, and the location of sampling efforts. The highest
PCB concentrations occur in the upper end of the estuary, in the
vicinity of the Aerovox Incorporated plant. This is also the
location which has received the highest intensity of sampling.
PCB concentrations measured in the area are primarily in the
1,000 to 5,000 ppm (dry weight) range, with some measurements
above 10,000 ppm, and some below 1 ppm. Thus, PCB distribution
in this highly contaminated area is somewhat “patchy”. It may be
that the mud flats along the shore of the river contain pockets
of PCB—laden oils in some places, whereas other portions of the
river have been swept relatively clean. Variations in measured
86
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U.S. ENVIRONMENTAL PROTECTION AGENCY
METCALF & EDDY, INC.
FIGURE 5. COLOR—CODED COMPUTER GRAPHICS — LEGEND
N
CONCENTRATION
50— 100
10—50
5—10
1—5
BELOW 1
ABOVE 10,000
5,000—10,000
1,000—5,000
500—1,000 1
100—500
One Kilometer
PPM DRY WEIGHT
liii sill I I I
-------
Aerovox
/1
/
0
FIGURE 6. AROCLOR 12148 IN
SURFACE SEDIMENTS, SAMPLING
LOCATIONS IN UPPER ACUSHNET
ESTUARY
S
o•
0
S
S
0
..
-------
I
. . .
.
.
S
••
FAIR HAVE N
FIGURE 7. AROCLOR
121$8 IN SURFACE
SEDIMENTS, SAMPLING
LOCATIONS IN
MIDDLE ACUSHNET
ESTUARY
S
.
0
-------
Aerovox
FIGURE 8. AROCLOR 125Z IN
SURFACE SEDIMENTS, SAMPLING
LOCATIONS IN UPPER ACUSHNET
ESTUARY
.
Sc
S
S.
-------
•.
S..
I 1 19
S
FAIRHAVEN
FIGURE 9. AROCLOR
125 I IN SURFACE
SEDIMENTS, SAMPLING
LOCATIONS IN MIDDLE
ACUSHNET ESTUARY
•••
.
S
S
S
S
.
S
S...
I
S..
...
S
S S
S
S
-------
Ae rovox
FIGURE 10. AROCLOR 125k IN
SHALLOW SEDIMENTS, SAMPLING
LOCATIONS IN UPPER ACUSHNET
ESTUARY
S.
S
S
.
•o
S
-------
.
FAIRHA YEN
. .
S
FIGURE 11. AROCLOR
125 t IN SHALLOW
SEDIMENTS, SAMPLING
LOCATIONS IN MIDDLE
ACUSHNET ESTUARY
S
S
0
• .
S
-------
FIGURE 12. AROCLOR 12514 IN
DEEP SEDIMENTS, SAMPLING
LOCATIONS IN UPPER ACUSHNET
ESTUARY
Aerovox
••.
S
S
.
-------
S
.
FAIRHAVEN
FIGURE 13. AROCLOR
12511 IN DEEP
SEDIMENTS, SAMPLING
LOCATIONS IN MIDDLE
ACUSHNET ESTUARY
S
S
.
S
S
S
S
S
S
-------
PCB concentrations may also be due to inconsistency in the
analyses. More precise delineation of “hot spots” in the
immediate vicinity of Aerovox Inc. may warrant further sampling
for cost—effective remedial action.
Samples taken throughout the remainder of the Inner New
Bedford Harbor (north of the hurricane barrier) are fairly evenly
distributed, as are their associated PCB concentrations. Between
the Coggleshall Bridge and the “hot spot” near the industrial
complexes, concentrations are predominantly in the range of 10 to
500 ppm (dry weight). Along the narrow neck south of the
industrial complex, there is a one kilometer stretch of river
which has been sampled considerably less than the rest of the
harbor, thus concentrations there remain relatively undefined.
From the Coggleshall Bridge south to the hurricane barrier, PCB
concentrations measured have almost all been less than 100 ppm
(dry weight), but greater than 1 ppm.
In the Outer Harbor (south of the hurricane barrier) and
in Clark’s Cove, sediment sampling has been less extensive. The
areas offshore of Cornell—Dubilier Electronics, the New Bedford
sewage treatment plant at Clark’s Point, and the combined sewer
overflows in Clark’s Cove have received the highest density of
sampling, and all three locations have sediment PCB concentra-
tions in the range of 5 to 50 ppm (dry weight). The remainder of
the estuary, although sparsely sampled, has PCB concentrations
mostly less than 5 ppm (dry weight), with only a few samples
falling into higher ranges.
96
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In an effort to apply the data regarding PCB concentra-
tions in one location In the estuary to other unsampled
locations, a geostatistical modelling concept known as “Kriging”
was used to develop color contour maps of the estuary. This
approach entailed the development of a “data semi—variogram” to
evaluate the continuity of the data, then fitting a model to it
which defined a radius for interpolation (Royle et al., 1981;
Olea, 19714). This method enables the user to define barriers
between points and to limit the model to “assumptions” which are
statistically more valid. With respect to the Acushnet Estuary,
this provided for definition of land barriers to PCB transport
(e.g., the hurricane barrier), such that points on one side of a
piece of land did not influence those on the other side in
interpolation. In addition, portions of the estuary where data
were too sparse and inconsistent for valid interpolation were
identified as “undefined” and no contours drawn (these areas
appear black on the maps).
Color contour maps using the Kriging approach were
generated for the same four data sets as the color point maps:
Aroclor 12148 in surface sediments, and Aroclor 12514 in surface,
shallow and deep sediments (Figures 114 through 21, See legends on
Figure 5). These data sets were the only ones with efficient
sampling points to develop contours.
As with the color point maps, several trends in the data
become immediately evident in viewing the contour maps. The most
striking fact is that the most severe contamination is restricted
97
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FIGURE 1 4. CONCENTRATION
CONTOURS, AROCLOR 12118 IN
SURFACE SEDIMENTS OF THE
UPPER ACUSHNET ESTUARY
Aerovox
-------
Pope’s
Isi.
FAIRHAVEN
FIGURE 15.
CONCENTRATION
CONTOURS, AROCLOR
12118 IN SURFACE
SEDIMENTS OF THE
MIDDLE ACUSHNET
ESTUARY
-------
Aerovox
FIGURE 16. CONCENTRATION
CONTOURS, AROCLOR 125k
IN SURFACE SEDIMENTS OF THE
UPPER ACUSHNET ESTUARY
-------
Pope’s
Isi .
FAIRFIA YEN
FIGURE 17.
CONCENTRAT ION
CONTOURS, AROCLOR
12514 IN SURFACE
SEDIMENTS OF THE
MIDDLE ACUSHNET
ESTUARY
____ 1
-------
FIGURE 18. CONCENTRATION
CONTOURS, AROCLOR 125 IN
SHALLOW SEDIMENTS OF THE
UPPER ACUSHNET ESTUARY
Ae rovox
-------
FAIRHAVEN
Pope’s
IsI.
FIGURE 19.
CONCENTRATI ON
CONTOURS, AROCLOR
125i4 IN SHALLOW
SEDIMENTS OF THE
MIDDLE ACUSHNET
ESTUARY
_________ _Th
-------
FIGURE 20. CONCENTRATION
CONTOURS, AROCLOR 125k IN
DEEP SEDIMENTS OF THE
UPPER ACUSHNET ESTUARY
Aerovox
-------
1 PoDe’s
sI.
FAIRHA YEN
FIGURE 21.
CONCENTRATION
CONTOURS, AROCLOR
12514 IN DEEP
SEDIMENTS OF THE
MIDDLE ACUSHNET
ESTUARY
1: ’
-------
to the upper estuary, north of the Coggleshall Bridge. The high
PCB concentrations in that area appear to emanate from the
industrial complexes on ‘he western shore of the river. In
addition, some trapping of’ sediment PCBs behind land barriers at
the bridges, and particularly at the hurricane barrier, Is
indicated.
Comparing the six maps of Aroclor 125k concentrations
(Figures 16 through 21), the highest concentrations in the upper
estuary are in the shallow sediments, II to 8 cm deep. This is
probably due to the fact that PCB discharge to the estuary was
ended in 1977, and the most contaminated sediments have been
covered by cleaner sediments since then. In the outer portions
of’ the estuary, higher concentrations appear on the maps in the
surface sediments than in deeper sediments. However, comparing
the sampling point maps shows this to be because very few subsur-
face sediment samples were collected in the areas of highest
surface sediment PCB concentration; around the treatment plant
outfalls, the discharge pipe from Cornell—Dublier Electronics,
and the CSO’s in Clark’s Cove. Thus, concentrations in the
shallow and deeper sediments in these three areas are unknown.
Given the historical deposition pattern Indicated in the upper
estuary, these subsurface sediments may be even more contaminated
than the 10 to 50 ppm (dry weight) of PCBs in the surface
sediments, and than the less than 5 ppm which they are shown to
be on the contour maps. Consequently, additional sampling in
106
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shallow and deep sediments in these areas is prescribed for
development of effective remedial action.
To some extent, data gaps uch as these are identified by
the Krlging process, in the black “undefined” areas predominating
in the outer estuary. However, as with any statistical model,
interpretation of these contour maps must be approached with
caution. The contours portray the average concentration measured
within an area of approximately 2,500 square meters. Thus, they
tend to smooth out some of the patchiness of the data. Given the
high variability in PCB analysis and the relative imprecision of
sample location, this results in a more conservative approach.
However, a few extremely high measurements do tend to inflate the
average concentration shown for a given area (e.g., at the
northern end of the estuary). In addition, PCB levels are
portrayed by the model as emanating from a source in all
directions; a more detailed transport modeling is required to
determine the actual direction(s) of travel. Consequently, these
contour maps would best be used in conjunction with the point
maps portraying the individual sample locations; the actual data
listed in the data base file; and a reliable model of PCB
transport in the estuary. Used in this manner, they provide an
invaluable management tool in portraying the location of PCB
contamination throughout the Acushnet Estuary.
Specific Contaminants Present
As is shown in Table 19, almost half of the PCB analyses
conducted on samples from the Acushnet Estuary area have been
107
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TABLE 19. PCB ANALYSES IN “RELIABLE” DATA BASE
No. Data
PCB Blend(s) Records
Aroclor 1016 338
Aroclor 1221 227
Aroclor 1232 227
Aroclor 12142 1420
Aroclor 12148 295
Aroclor 12514 12146
roc1or 1260 2514
Aroclor 1262 148
Aroclors 1016/12142 27
Aroclors 12142/12514 31
Aroclors 12148/12514 1 13
“Total” PCBs 714
-------
quantitated in terms of Aroclor 1251$, implying that the distribu-
tion of PCB isomers in the samples taken are distributed on a gas
chromotogram in a configuration most similar to the Aroclor 1251$
standard. The data presented earlier in Tables 17 and 18,
however, indicate that PCBs resembling the Aroclor 12148
configuration are also present in high concentrations in the
estuary, perhaps even higher than as Aroclor 12514. Interestingly
enough, neither of these commercial PCB mixtures was ever used in
large quantities by the local industries. The two capacitor
manufacturers in New Bedford, Cornell—Dubilier Electronics and
Aerovox Incorporated, used primarily Aroclor 12142 prior to 1971,
replacing it with Aroclor 1016 until 1977. Aroclors 12514 and
1252 were used in les8er quantities (Weaver, 1982). Even so, the
measurements which have been made of the lower chlorinated
Aroclors 12142 and 1016 reveal significantly lower concentrations
in the estuarine sediments and biota than measurements of
Aroc].ors 12148 and 12514. There are no data on Aroclor 1252
concentrations.
The fact that most of the PCB analyses have been
quantitated in terms of Aroolor 12514 may be due to the fact that
many labs use that standard as common practice, not necessarily
because it is most applicable to the sample chromatogram.
Farringtori et al. (1981) expressed concern that this was the case
and that, since they were finding mostly Aroclors 1016 and 12142
in the Acushnet Estuary sediments, the state of the art methods
which measured only 1251$ were low by a factor of two or more.
109
-------
However, the high concentrations that have been measured using
both the Aroclor 12118 and 12514 standards indicate that the PCBs
present in the Acushnet Estuarine sediments do actually fall
within the range of isomers represented by these two standards,
thus the measurements are not low. This may be the result of
degradation of the lower—chlorinated Isomers in the environment,
driving the average chlorine content of the mixture up. Similar
historical changes in PCB composition have occurred In other
estuaries (Stainken and Roliwagen, 1979; Butler and Schutzmann,
1978). In the upper reaches of the Hudson River, New York,
Aroclors 12142 and 1016 constItuted 90 percent of’ the PCBs
measured, with Aroclor 12514 making up the rest. The relative
percentage of Aroclor 12514, however, increased downstream
(further from the PCB sources) to approximately 20 percent of the
total (Bopp et al., 1981).
In contrast to the estuarlne data, samples of wastewater
collected from the New Bedford sewer system revealed Aroclor 1016
In higher concentrations than Aroclor 12514, and in the treatment
plant sludge and effluent samples only Aroclor 12142 was found.
Similarly, PCB concentrations In air samples mostly occurred as
Aroclors 1016/12142, with very little Aroclor 12514. (Aroclors
1016 and 12142 are very similar In chlorine composition, with
averages of 141 and 142 percent respectively, and often are not
distinguishable on a chromatograph). Since the different Aroclor
mixtures do not represent discrete compounds, but rather an
average chlorine composition, their distinction here is made
110
-------
essentially for purposes of quantification and evaluation of the
overall PCB contamination problem. The distinction can not be
applied when it comes to remedial action as the individual
Aroclors can not be isolated, nor can it be used to conclusively
link the contamination with PCB sources, due to the changes in
composition which can not be quantified.
In addition to its extensive PCB contamination, the
Acushnet Estuary has significantly high levels of trace metals,
particularly chromium, copper, lead and zinc. It has been
estimated that the three major contaminant metals, copper,
chromium, and zinc, form more than one percent of the dry weight
of harbor sediments (Summerhayes et al., 1977). Tables 20 and 21
summarize the metals concentrations in estuarine sediments, based
on the data presently maintained in the data base file. It
should be noted, however, that the metals data in the file are
only those collected in conjunction with PCB5 (since that was the
focus of this project), and do not constitute a comprehensive
metals data base. Other available metals data should be obtained
and incorporated into the system. With a larger metals data
base, contour maps, like those for the PCB concentrations, could
be developed to determine whether the locations of’ metals
contamination coincide with the PCB hot spots. It will be
especially important in evaluating cleanup alternatives (e.g.
dredging) to know where and to what extent heavy metals are
present in the estuary, as they may be more easily mobilized in
111
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TABLE 20. METALS CONCENTRATIONS IN INNER HARBOR
SEDIMFNTS (PPM DRY WT.),
ACUSHNET ESTUARY
— No. of
Metal Records Minimum Maximum Mediar Mean
Arsenic 514 0.1 ii6 6.14 12
Cadmium 514 ND 65 14.0 8.7
Chromium 514 3.9 9140 110 210
Copper 514 5.3 2200 335 560
Lead 514 2.1 11400 195 320
Mercury 514 ND 214 0.3 0.9
Nickel 514 0.1 193 28 140
Selenium
Silver 33 ND 11437 1.9 145
Vanadium 22 5.14 150 32 143
Zinc 53 10 141400 290 700
-------
TABLE 21. METALS CONCENTRATIONS IN OUTER HARBOR
SEDIMENTS (PPM DRY WT.),
ACUSHNET ESTUARY
No. of
Records Minimum Maximum Median Mean
Metal
Arsenic
——
——
——
——
——
Cadmium
17
ND
23
1.1
2.7
Chromium
17
14.3
263
27
57
Copper
17
11.7
1437
614
110
Lead
17
7.1
11111
511
120
Mercury
17
ND
11.3
0.2
0.7
Nickel
——
——
——
——
——
Seierdur:
17
3.3
33
7.6
11
Silver
——
——
——
——
——
Vana 1um
17
2.11
65
22
29
Zinc
17
13
693
117
180
-------
the water column, may influence chemical reactions, and can also
be extremely toxic.
There are presently no data in the system for
polychiorinated dibenzofurans (PCDFs), polychiorinated
naphthalenes (PCNs), polychlorinated quarterphenyls (PCQs), or
polychlorinated dibenzo—dioxins (PCDDs), which have been
implicated as possible contaminants and/or byproducts of PCBs.
Due to the highly toxic nature of’ these compounds, several
samples from a variety of Acushnet Estuary media (e.g. sediment,
air, water) should be screened for their presence.
Critical Pathways and Fate Processes
A thorough understanding of critical pathways and fate
processes is probably one of the most significant “data gaps”
remaining in the Acushnet Estuary PCB issue. Although the
existing data base provides a description of the PCB
contamination of the Acushnet Estuary, it is a dynamic and ever—
changing situtation. In order to evaluate the significance of
this contamination, it is essential to identify the processes by
which it is changing, and to determine which sectors of the
environment are most in need of remedial action. This need has
been recognized, and a comprehensive program for the
investigation of biological, chemical, and geophysical pathways
in the harbor has been outlined in project work statement 007 of
the RAMP document (Weston, 1983). The existing data base will
provide the foundation for this endeavor, and apparent trends
which are described here will be investigated more fully.
liii
-------
The most significant PCB contamination in the Acushnet
Estuary is in the bottom sediments of the Inner Harbor. In spite
of the large amount of data for this area, there is presently
very little known about the physical processes responsible for
the transport and disturbance of these sediments. One study
(Summerhayes et al., 1977) dealt primarily with the transport of
heavy metals (and not PCBs) in the Outer Harbor and western
Buzzards Bay. This research revealed some of the significant
fundamental processes relevant to PCB transport. It determined
that silt and clay from outer Buzzards Bay are transported into
the harbor and trapped by the hurricane barrier at a rate of
approximately 1 to 8 cm/yr in the deeps, and < 2 cm/yr in the
shallows. Summerhayes et al. described the harbor as a “leaky
sink” for organic and industrial contaminants.
What remains to be defined by the proposed investigation
is how the sediments and thus the PCBs, are distributed and
redistributed within the Inner Harbor area. The contour maps
developed with the Kriging process indicate some accumulation of
PCBs behind the existing barriers, however, the extent of this
accumulation can not be quantified due to the paucity of data in
these areas. There is, for example, no data for any sediment
samples collected immediately to the north of the western segment
of the hurricane barrier, although this appears to be one of’ the
most likely places for sediment trapping to occur. The modeling
of sediment transport dynamics will require additional sampling
in these areas.
115
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Although there is a substantial amount of sediment PCB
data at present, there is relatively little information on the
inobiliza-tion of PCBs to, and subsequent transport in, the
estuarine water column. The analytical methods used in
quantitating water samples from the Acushnet Estuary in the past
did not permit detection of low, but highly toxic, levels of
PCBs. Since the water column moves differently than the
sediments (e.g. it is probably flushed more rapidly), and is a
ready source of PCBs to biological organisms, it merits further
investigation. Additional water sampling will also indicate
whether (and where) the bottom sediments are steadily “leaking”
PCBs to the water column, or whether they are being effectively
capped by the natural sedimentation of cleaner materials. The
few sediment elutriate data which exist at present will also be
informative in this matter, however they portray more the
potential for the sediments to leak PCBs to the water column than
the actual exchange dynamics which take place.
Tables 17 and 18 presented earlier (pages 77 and 78)
indicate the extent to which aquatic biota in the Acushnet
Estuary have bioconoentrated PCBs. Due to their high lipid
content and habitat, eels were the most severely contaminated of’
the organisms studied. Data on PCBs in lobsters and quahogs
(specifically in the Inner Harbor) need to be supplemented, with
investigation into the relation of PCB concentrations to organism
sex and size, and seasonal migrations. This would apply to any
other commercial fish species in the estuary, as there may be
116
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times during the year when contamination Is less severe and
harvesting would be less of a risk to public health.
Also indie ted, but not yet clearly defined, by the data
base is the apparent degradation of PCBs (specifically the lower
chlorinated isomers) in the estuarine environment. Photolytic
decomposition and biodegration may be occurring, for example, in
both the aerobic and anaerobic portions of the mudflats lining
the estuary. Similarly, there has been very little effort made
to relate PCB concentrations in air to those of nearby sediments
and surface waters, such that the volatization from such sources
could be quantified. It is anticipated that the significance of
this and other PCB pathways will be identified in the modeling
investigations.
Implications of Contamination
Table 22 presents a summary of the regulatory limits and
standards relevant to PCBs. The Toxic Substance Control Act
(TSCA), I0 CFR Part 761, defines a PCB - contaminated waste as one
that contains PCBs at a concentration between 50 and 500 ppm, and
a PCB waste as that which contains PCBs greater than 500 ppm.
TSCA (LW CFR Part 761.65) also provides extensive requirements for
storage of PCBs in concentrations exceeding 50 ppm, including
specifications for storage facility, the PCB containers, handling
equipment, marking of PCBs, a Spill Prevention and Control Plan,
and location at a site not below the 100 year flood plain. Based
on the information presented in Figures 1 4 through 21, a
substantial portion of the sediments underlying the Inner New
117
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TABLE 22. PCB LIMITS AND STANDARDS
Regulation/
Controlling Agency Media Level Action
TSCA, PCB—contaminated 50—500 ppm must be disposed of
(10 CFR, Part 761) waste (dry weight) by chemical waste
landfilling or Annex I
incineration.
PCB waste > 500 ppm must be disposed of by
(dry weight) Annex I incineration.
USFDA Foodstuffs:
(J 4 i CFR, 57389, fish & shellfish 5.0 ppm maximum allowable level
1979) (edible portion) (wet weight) for the protection of
public health.
red meat 3.0 ppm maximum allowable level
(fat basis) (wet weight) for the protection of
public health.
poultry 3.0 ppm maximum allowable level
(fat basis) (wet weight) for the protection of
public health.
EPA Criteria, Ambient Water 0.01 4 .g/l maximum level for pro—
1981 (P.L. 95— tection to freshwater
317, Section fish.
3 0 1 4(a)(1)
0.030 .g/l maximum level for pro-
tection to saltwater
fish.
0.000 /l maximum level for pro-
tection to human health.
NIOSH Workroom air 1 .g/m 3 maximum recommenced con—
centration for protec-
tion of health.
‘USFDA lowered this standard to 2 ppm in 1979, however challenges by the seafood industry
have resulted in a temporary stay placed on the standard by the courts.
118
METCALF a EDDY
-------
Bedford Harbor are categorized as PCB wastes and PCB—contaminated
wastes under TSCA. The fact that any of this material dredged
from the harbor will require special disposal as a hazardous
waste will have significant implications as to the cost and
efficiency of employing dredging as a remedial action.
Based on the data summarized in Tables 17 and 18, median
PCB concentrations in eels and lobsters in the Acushnet Estuary
are well above the FDA action level of 5 ppm, which is the
maximum PCB concentration considered safe for human
consumption. Although there are no lobster data for the Inner
Harbor, this can be assumed to apply to both the Inner and Outer
Harbor areas. PCB concentrations in lobsters taken from further
out into Buzzards Bay are also higher than 5 ppm. The median PCB
concentration in winter flounder is above the FDA limit only in
the Inner Harbor, although in the Outer Harbor, flounder PCB
concentrations are above FDA’S recommended limit of 2 ppm.
Median PCB concentrations in quahogs from these areas are not
above the FDA limit, however there are only three data records
for quahogs in the Inner Harbor area.
Based on these data summaries, the fishing closure areas
established by the Massachusetts Department of Public Health
appear to be appropriate. These closures prohibit all fishing
activity in the Inner Harbor area (Area 1); fishing for lobsters,
eels, flounder, tautog and soup in the Outer Harbor area (Area 2,
extending to the Ricketsons Point/Wilbur Point transect): and
lobster fishing inside of Negro Ledge (Area 3).
119
METCALF a
-------
The EPA criteria for PCB in ambient water are 0.01 4 ugh
to protect freshwater fish, 0.030 ugh to protect saltwater fish,
and zero for maximum protection of human he lth (U.S. EPA
1980). These concentrations are average 2 1 4—hour values. Ambient
water PCB concentrations measured in the Acushnet River in 1981
were mostly “non detectable”, but were based on a detection limit
of 0.5 ugh. Measurable concentrations ranged as high as 6.1
ugh. Thus, the average 2 1 t—hour concentration of PCBs in the
Acushnet Estuary waters may well be far in excess of the EPA
criteria.
Effectiveness and Impacts of Potential Cleanup Alternatives
The color contour maps portraying PCB concentrations in
the sediments of the Acushnet Estuary (Figures 1I through 21)
delineate several “hot spot” areas applicable to fast track
remedial action. The maps also indicate that the most severely
contaminated sedments lie approximately 1 to 8 cm deep, an
important fact in planning remedial operations and in evaluating
the potential natural capping processes in the harbor.
The proposed modeling of sediment transport and PCB
dynamics for the estuary will provide much of the information
crucial to the planning of remedial action alternatives. In
addition, the further resolution of’ sediment PCB concentrations
in areas not well sampled, and the addition of’ more metals data
to the data base, will permit the development of more
comprehensive, and statistically significant, contour maps
delineating areas requiring remedial action.
120
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135. Thomari .R.V. 1981. Equilibrium model of fate of
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136. Tucker, E.S. et al. 1975. Migration of polychiorinated
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Environ. Contam. Toxiool. 13(1).
137. Turk, J.T. 1980. Applications of Hudson River basin PCB
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Contaminants and Sediments, Vol. 1. Fate and Transport
Case Studies, Modeling, Toxicity. Ann Arbor Science, Ann
Arbor, MI. 558pp.
138. Urabe, H., H. Koda, and M. Asahi. 1979. Present state of
Yusho patients. Pages 273—276. In: W.J. Nicholson and
J.A. Moore, eds. Health Effects of Halogenated
Hydrocarbons. Annals of the New York Academy of
Sciences. Vol. 320.
139. Urey, J.C., J.C. Kricher and J.M. Boylan. 1976.
Bioconcentration of four pure PCB isomers by Chlorella
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1 311
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1110. U.S. EPA. 1976a. Quality criteria for water. Washington,
D.C. July 1976.
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and environmental distribution. Task 1, Final Report
Office of Toxic Substances. Washington, D.C. EPA—560/6—
76—005.
1112. U.S. EPA. 1976c. National conference on polychlorinated
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00k.
1113. U.S. EPA. 1977a. Evaluation of the problem posed by in—
place pollutants in Baltimore Harbor and recommendations
of corrective action. EPA Office of Water Planning and
Standards, Washington, DC EPA— 1 1110/5—77—015B.
11111. U.S. EPA. 1977b PCBs removal in publicly—owned treatment
works. Criteria and Standards Division. Washington, DC
EPA 11110/5—77—017
1115. U.S. EPA. 1980. Ambient water quality criteria for
polychiorinated biphenyls. Office of Water Regulations
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1116. Uthe, J.F., H.C. Freeman and A.D. McIntyre. 1980. Con
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Klauda et al., 1981.
1147. Vieth, G.D., D.W. Kuehi, F.A. Puglisi, G.E. Glass, and J.G.
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75—00 1 1.
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136
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137
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APPENDIX A
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APPENDIX A
DATA PIANAGENEN1 SYSTEN
SUP1) AR! OF FILE CONTENTS
Sample Types
Air
Aquatic biota
Argopecten irradians (Bar scallop)
Anguilla rostrata (Ar erican eel)
Cerianthus americanus (polychaete)
Callinectes sapidus (Blue crab)
Centropristis striata (Black seabass)
Crassostrea virginica (American oyster)
eukcnsia demissa (Bibbed mussel)
Hoinarus aniericanus (American lobster)
loligo peali (Long—finned squid)
Mya ar naria (Softshell clam)
Nerluccius bilinearis (Silver hake)
Nu telus canis (Smooth dogfish)
Nytilus edulis (Elue mussel)
Nercenarja mercenaria (Quahog)
Norone saxatilis (Striped bass)
Nephtys incisa (polychaete)
Neopanope texana (Nud crab)
Osmerus mordax (American smelt)
Pseudopleuronectes americanus (Winter flounder)
Irionotus carolinus (Sea robin)
raralichthys dentatus (Summer flounder or Fluke)
laralichthys oblongus (Fourspot flounder)
Fomatoinus saltatrix (Bluefish)
Peprilus triacanthus (Butterfish)
Raja erinacae (Little skate)
Scophtha]niiis aquosus (Windowpane)
Stenctonus chrysops (Scup)
Tautogolabrus adspersus (Cunner)
Tautoga onitus (‘Iautog)
Urophyciz chuss (Red hake)
Grit
)ii cellaneous
Sediment
Sediment elutriates
Sediments — EP Toxicity
Soil
Waste
Waste - EP Toxicity
Water
A-i
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Sample Sources
S nne e a — a a
Ambient air
Apponcgansett River Pasin
A sh
Buzzards Bay
Clarks Cove
Cooling water
Edible meat (eg. lobster claw)
Flesh
Grit
Groundwater
Inner Harbor (New Pedfcrd)
Industrial vastevater
Land
P ount Hope Pay, Fall River
Niscellaneous
Outer Harlor (New Bedford)
Paw drinking water
River
Raw vastevater
Si u dg e
Treated wastewater
Viscera
Whole organism (without shell)
Waste
General vastevater
Exact Sources
— — aflaa aflfl
Deep (>8 cm for sediments)
Downwind
Mid-depth (‘ater)
Shallow (li—8 cm for sediments)
At the source (air)
Surface (0—1 1 ci i i for sediments)
Upwind
Un its
No units( or non—detectable)
Millivolts
Nanograms per cubic meter
Parts per million (ppm)
Parts per million (ppm) dry weight
Parts per million (ppm) wet weight
A-2
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Parameters
PC Bs
Aroclor 1221
Aroc]or 1232
Aroclor 1016
Aroclor 1242
Aroclor 1248
Aroclor 1254
Aroclor 1260
Aroclor 1262
Aroclors 1242/1016
Aroclors 1242/1254
Aroclors 1248/1260
Aroclors 1248/1254
non—specific PCBs
Total PCPs
ret al s
Arsenic
Cadmium
Chromium
Co pp sr
lead
barium
Mercury
Nickel
E len ium
Li lv e r
Thallium
Zinc
Cobalt
Iron
Vanadium
Miscellaneous
Chemical Oxygen Demand
edox potential
Ci i L grease
Fhencl
A-3
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Data Ccllecting Agencies
Army Corps of Engineers
Aerovox Incorporated
Camp, Dresser C McKee
Cornell-Dub]ier Electronics
Jason Corte].l Associates
Massachusetts Office of Coastal Zone Management
? assachusetts Department of Environmental Quality Engineering
Livision of Water Pollution Control
Massachusetts Division of Marine Fisheries
U.S. Environmental Protection Agency -— Region I
Pairbaven Marine
U.S. Food and Drug Administration
GCA Ccrporation
Gidley Laboratories
Nassachusetts Department c i Public Health
Yessachusetts Department of Public Works
New England Governor’s Conference, Inc.
Scutheastern ? assachusetts University
!Iibbetts Engineering Corp.
University of South Carolina
oods Hole Oceanographic Institute
Analytical Laboratories
Cambridge Analytical Associates
Cat Ccve Marine Lab (DMF)
Camp, Dresser McKee
Jason H. Cortell C Associates
U.S. EPA -— Region I (Lexington, NA)
Fnergy esources Company
Environmental Science C Engineering
FDA —— Boston District Cffice
GCA Corporation
Cidley Laboratories
Lawrence Experiment Station (DEGE)
Lycott Environmental Research, Inc.
rassachusetts Department of Public Health
Monsanto Corporation
New England Aquarium
New England Analytical C Testing Lab
Southeastern !assachusetts University
Tibbetts Fogineering Corpcration
University of South Carolina
U.S. Coast Guard
Versar
hoods Hole Cceanographic Institute
Woodscn — Tenet Laboratories
A-4
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Analytical Methods References
Gas chromatograph with electron cat -ure detector.
IJSFDA Pesticide Analytical Manual Vol. 1, Revised
periodically from 1968—1982.
Gas chromatograph with electron capture detector;
mass spectrophotometer.
Methods for PCB’s in Industrial Effluent IJSEPA, NFRC,
1973.
Gas chrowatcgraph with electrcn capture detector;
Method for Organochiorine and Organophosphorus.
Pesticides in Soil, EPA/Pesticide Monitoring Laboratory,
Building 1105 NSTL/NASA, Bay St. Lcuis, MI.
Gas chroinatograph vith electron capture detector;
Manual of Analytical Methods for the Analysis of
Pesticides in Humans and Environmental Samples.
USEPA, June, 1980 EPA 6O0/8—B— 38.
Gas chromatograph with electron capture detector.
American Association of Analytical Chemists, 13th Edition,
1980, Sect. 29.001—29028.
Gas chromatograph with electron capture detector;
mass spectrophotometer.
Denver Method for Chlorinated Pesticides in Surface
Waters, USEPA, NFIC.
Gas chromatograph with electron capture detector;
mass spectrophotometer.
Determination of Total PCB Emissions from Municipal and
Industrial Effluents, USEPA, 1976.
Gas chromatograph with electron capture detector.
ASTA Method P3534; Standard Test for PCBs in water
(Revised annually).
Gas chromatograph with electron capture detector;
mass spectrophotometer.
USFDA Pesticide Analytical Manual Vol. 1, Revised 1979;
Sections 212.13(a), 212.14(d) with modification.
GaE chrotnatograph with electron capture detector.
Manual of Analytical Methods for the Analysis of
Pesticide Residues in Human and Environmental Residues
Section iC A, USEPA, 1974.
A-5
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Gas chromatograph with electron capture detector.
Guidelines establishing test procedures for the analysis
of pollutants; proposed regulations:
Method 608 -— organo—chioride pesticides and PCBs,
USEPA, 1979, Federal Register 414(233):69501—69509.
Gas chromatograph with electron capture detector.
Standard Methods for the Examination of Water and
Wastewater, Supplement to the 15th Edition, III C, p. 5—78,
APHA, AWWA, WPCF, 1980.
Gas chromatograph with electron capture detector.
Methods fcr evaluating Solid Wastes, Physical and Chemical
Methods, 8.86, EPA, 1980.
Gas chromatograph with electron capture detector.
Extraction of PCBs from Air Dried ediwents with Soxhlet
A paratus. USEPA, 1981 and P. Coates, 08/04/81
(letter tc C. Parker, PCB analysis of lobsters).
Gas chromatcgraph with electron capture detector.
Chemistry Manual for Bottom Sediments and Elutriate
Tasting, EPA—905/U—79—014, March 1979.
Gas chromatograph with electron capture detector.
Analytical Services for PCBs in Environment and Industrial
Matrices, ‘Jersar Inc., Dec. 1981.
Gas chromatograph with electron capture detector.
The Analysis of PCB in Transformer Fluid and Waste Oil,
EFA/EMLS Cffice of Research and Development, Cincinnati,
OH, 6/24/80 and Proposal of a Technique for the Analysis
of PCBs in Mineral Insulating Oils, PCB 298, 34—2, ASIM
Committee D-27, Received May, 1980.
Gas chromatograph with electron capture detector.
Method for Organopesticides and PCBs in Urban Soil,
EPA/Toxicant Analysis Center, Bay St Louis, MI, 1979 and
Nacrodnalysis Of Polychlorinated Piphenyls, EPA/NEIC,
renver Co. 10/29/80 and Methods of Analysis, AOAC,
29.013, 13th Edition, 1980.
Gas chromatograph with electron capture detector.
Hydrocarbcns, Polychiorinated Piphenyls and DDE in
Mussels and Oysters from the U.S. Coast, 1976-1978,
Technical Report no. WNOI-82—182, Wcods Hole Oceanographic
Institute, October 1982.
A-6
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Gas chromatograpy, liquid chromatography and thin layer
chromatography (the reported concentrations represent
a consensus value of the three methods).
(a) CO DT (C—DNT—4/54) ltr 3913 Ser: 14—1202V of 11 Nai h
1982, Letter report from Commanding Officer, CC Research
and Development Center, to Commanding Officer, CC !!arine
Safety Office, Providence. RI.
Acushnet River sediment sample analysis report, 6/11/82.
Cas chromatography with electron capture detector, mass
spectrophotometer verification of selected samples.
Correspondence from % HOI (Alan C. ( ‘avis) to ? etca1f 1 Eddy
(P.3. Reirold), 3/11/83.
Gas chromatograpy, liquid chromatography and thin layer
chromatography (the reported concentrations represent
a consensus value of the three methods).
(a) CC,B&DC ltr 72415 14.3 of 11 June 1982, Letter report
from Commanding Officer, CC Research and Development
Center, to Commanding Officer, CG Marine Safety Office,
Providence, RI.
Acushnet Fiver Sediment Sample Analysis Report,
1 obile laboratory, 7/1/82.
A-7
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