EPA/902-R-03-002
December 2003
Final Report
SEDIMENT QUALITY OF THE NY/NJ
HARBOR SYSTEM: A 5-Year Revisit
1993/4-1998
An Investigation under the Regional Environmental Monitoring and Assessment Program
(REMAP)
Darvene Adams
USEPA-Region 2, Edison, NJ
Sandra Benyi
USEPA-ORD, Narragansett, Rl
-------
Disclaimer
The use of product or trade names does not indicate endorsement by the U.S. Environmental
Protection Agency. Reference to or use of various guidelines or threshold values does not constitute a
policy decision by the U.S. EPA to adopt these values as criteria or standards.
-------
FOREWORD
The Environmental Monitoring and Assessment Program (EMAP) is a long-term, interagency
environmental monitoring and research program overseen by EPA's Office of Research and
Development (ORD). Its goal is to provide the public, scientists and Congress with information that
can be used to evaluate the overall condition of the Nation's ecological resources. The program is
designed to operate on a broad geographic scale.
EMAP has entered into partnerships with EPA Regional offices, other Federal agencies and States to
assess environmental quality at smaller, regional or local scales. These Regional EMAP (REMAP)
projects adapt the EMAP approach to assess specific areas more precisely than can be accomplished
by existing data or EMAP alone. These projects also provide the opportunity to apply EMAP's
statistical design and ecological indicators at localized scales.
111
-------
EXECUTIVE SUMMARY
The Comprehensive Conservation and Management Plan (CCMP) for the NY/NJ Harbor
requires specific management actions to maintain and restore the Harbor environment. It also
specifies that the progress of these management actions on the improvement of sediment quality
and biological condition in the Harbor be measured. To do this requires initially establishing a
baseline of condition of the Harbor sediment that is objective and of known statistical
confidence. The next logical step is to periodically determine whether conditions have
improved, declined or remained the same from the baseline. Existing studies either were
conducted in a biased manner, did not cover all portions of the Harbor or did not concurrently
collect the biological and chemical information to do be able to provide the baseline or
subsequent trend assessment.
A previous investigation (Adams et al., 1998) provided a baseline of the areal extent of chemical
contamination and biological effects in the NY/NJ Harbor system. That investigation, done in
1993 and 1994, also defined the extent of specific biological effects, such as degraded benthic
macroinvertebrate communities and amphipod toxicity, and determined that these effects were
associated with specific contaminants found in the sediments of the Harbor.
To begin to define trends in sediment quality and biological health of the Harbor, EPA-Region 2
conducted a followup investigation in 1998. The design, parameters measured, and methods
were identical to, or comparable to, the 1993/1994 investigation. Synoptic measurements of
benthic macroinvertebrate assemblages, sediment toxicity and sediment chemical concentrations
were collected in four sub-basins of the Harbor, encompassing 28 sampling stations in each sub-
basin. Surficial sediment contaminant concentrations, sediment toxicity (Ampelisca abditd) and
benthic macrofaunal community structure were measured at each station.
Some improvements in the mean values for chemical contaminants in the Harbor's sediment
have occurred between 1993/4 and 1998. Sediment chemistry results show the Harbor is still
extensively contaminated but the mean values for cadmium, chromium and chlordane have
declined. However, the Harbor means for mercury and DDT still exceed ERMs and all
chemicals that have ERLs exceeded these thresholds in the Harbor, except antimony and
cadmium. Newark Bay is still the most highly affected sub-basin but mean values for silver and
chlordane showed a significant decrease. In Upper Harbor, the total DDT mean had a
statistically significant decrease.
IV
-------
In terms of areal extent, chemical contamination is still widespread. In 1998, 45% of the Harbor
exceeded an ERM (compared to 50% in 1993/4), and 86% exceeded an ERL (87% in 1993/4).
While metals levels have remained the same, pesticide levels appear to be declining. Mercury
still is the most ubiquitous chemical at levels of concern. In 1998, 68% of the Harbor was above
the mercury ERL (75% in 1993/4) and 42% was above the ERM (34% in 1993/4). Newark Bay
is still the most extensively chemically contaminated sub-basin by area, followed by Upper
Harbor.
Sediment toxicity has remained the same between studies. In 1998, 12% of the Harbor was
considered toxic to the amphipod, Ampelisca abdita, compared to 15% in 1993/4. There have
been no statistically significant changes in sediment toxicity in any of the sub-basins. Newark
Bay and Jamaica Bay still have the most area of toxic sediments.
Some aspects of the benthic community health in the Harbor have improved between 1993/4 and
1998. The total number of species and species diversity have increased. The percent of
pollution-indicative species has significantly declined but the percent of pollution-sensitive
species has not shown a significant change. Benthic abundance and biomass have decreased
from 1993/4. The number of species increased in individual sub-basins, except for Upper
Harbor. Upper Harbor also saw a significant decrease in biomass.
Application of the benthic index developed in the baseline investigation (Adams et al., 1998)
showed that 31% of the area of the Harbor would be considered to have impacted benthic
communities, compared to 53% in 1998. While the amount of area in the most impacted
category has remained the same from 1993/4 to 1998, there is significantly more area of the
Harbor that is considered similar to reference in 1998. In the individual sub-basins (except for
Newark Bay), a shift is seen of area from the moderately impacted category to the least
impacted. Newark Bay had significantly more area move to the most impacted category in 1998
than in 1993/4.
It appears that some aspects of the sediment quality of the Harbor are beginning to improve
slightly. Future monitoring and research should focus on continuing the assessment of change in
Harbor sediment quality. There also should be emphasis on development and evaluation of
indicators that are more sensitive to the more subtle changes that may occur in the future and
identifying and controlling contaminants other than those currently measured that might be
responsible for the biological effects that have been seen.
-------
ACKNOWLEDGMENTS
Any investigation that involves a range of activities, in this case planning, design, implementation, data
analysis and interpretation, by necessity has the support and involvement of many people.
We would like to acknowledge Tony Olsen, Steve Schimmel and John Paul (USEPA-ORD) for
valuable and expert assistance with the design of this investigation. Randy Braun, Helen Grebe, Warren
McHose, and Steve Hale (all USEPA-Region 2) provided sampling logistics support and contributed
as field crews. Thuan Iran, Jim Kurtenbach, Bill Glynn, Tammy Nguyen, Pedro Gonzalez and Bob
Spillers (USEPA-Region 2) took time from their other duties to be part of the field crews. Jim Ferretti
and Diane Calesso conducted Ampelisca abdita assays. Erwin Smieszek filled in for field work and
supplied GIS products.
We are indebted to Kevin Summers and John Macauley (ORD-GB) for support with contract
mechanisms, as well as to Jawed Hameedi and Bernie Gottholm (NOAA) for access to NOAA
contract laboratories. Joe Livolsi (ORD-N) provided QA assistance, and Steve Hale (ORD-N)
provided database management and the internet availability of the data. Jim Heltshe (URI) provided
statistical direction, and Melissa Hughes (OAO Corp.) carried out numerous statistical analyses. Two
external reviewers and several internal reviewers provided essential peer review that strengthened the
final data analysis and interpretation as well as this report.
VI
-------
CONTENTS
Page
FOREWORD iii
EXECUTIVE SUMMARY iv
ACKNOWLEDGMENTS vi
INTRODUCTION 1-1
OBJECTIVE 1-2
ORGANIZATION OF THE REPORT 1 -2
METHODS 2-1
STUDY AREA 2-1
STUDY DESIGN 2-1
SAMPLING PROCEDURES 2-2
Water Column 2-2
Sediment 2-2
Benthos 2-2
LABORATORY METHODS 2-3
Major and Trace Elements 2-5
Organic Compounds 2-5
Sediment Physical Parameters 2-5
Vll
-------
TOXICITY METHODS 2-6
Ampelisca abdita Assays 2-6
BENTHIC MACROINVERTEBRATE ASSEMBLAGES 2-6
DATA ANALYSIS 2-7
Chemical Data 2-7
Toxicity Data 2-7
Benthic Macroinvertebrate Data 2-7
Condition Estimates 2-8
Mean Condition 2-8
Percent of Area Estimates 2-10
SELECTION OF THRESHOLD VALUES 2-10
Physical Data 2-10
Chemical Data 2-10
Sediment Toxicity Data 2-12
Benthic Index 2-12
PHYSICAL PARAMETERS 3-1
Depth 3-1
Percent Silt-Clay 3-1
Vlll
-------
Total Organic Carbon (TOC) 3-2
Water Column Profile 3-4
SEDIMENT CHEMISTRY 4-1
Mean Condition 4-1
Areal Extent 4-2
Dioxins and Furans 4-5
SEDIMENT TOXICITY 5-1
Mean Condition 5-1
Areal Extent 5-2
BENTHIC MACROINVERTEBRATES 6-1
Diversity and Taxonomic Composition 6-2
Abundance and Biomass 6-3
Benthic Index 6-4
SUMMARY AND RECOMMENDATIONS 7-1
Summary 7-1
Recommendations 7-3
REFERENCES 8-1
IX
-------
APPENDICES
A Station maps A-l
B B-l) Area-weighted mean concentrations for all sediment B-l
contaminants
B-2) Percent of area exceeding ERM values for all sediment
contaminants
C Lists of Pollution-tolerant and Pollution-sensitive benthic C-l
organisms for the Harbor
D Benthic Index values for individual stations D-l
LIST OF FIGURES
2-1 Stations in the study area 2-1
3-1 Percent of area distribution of substrate type 3-2
3-2 Percent of area distribution of TOC for the Harbor 3-3
4-1 Percent of area exceeding ERLs and ERMs for individual 4-3
chemical groups in 1993/4 and 1998
4-2 Percent of area greater than ERL and ERM values for 1993/4 4-3
and 1998 for metals in the Harbor
4-3 Percent of Harbor area greater than ERL and ERM values for 4-3
1993/4 and 1998 for organics in the Harbor
4-4 Percent of sub-basin areas greater than the mercury ERL and 4-4
ERM values of 1993/4 and 1998
-------
4-5 Distribution of mercury concentrations in 1998 by station 4-4
4-6 Distribution of total PAH concentrations in 1998 by station 4-4
5-1 Percent of area with Ampelisca toxicity 5-2
5-2 Distribution of stations with A. abdita toxicity 5-2
6-1 Numbers of benthic macrofaunal species, by major taxon 6-3
6-2 B-IBI scores of individual stations 6-4
LIST OF TABLES
2-1 Sub-basin areas 2-1
2-2 Summary of physical/chemical analytical methods 2-3
2-3 Analytical measurements for sediment samples 2-4
2-4 Benthic macroinvertebrate measures included in B-IBI 2-7
2-5 ERL and ERM concentrations for sediment trace metals and 2-11
organic compounds
3-1 Area-weighted means for depth 3-1
3-2 Area-weighted means of % silt-clay 3-2
3-3 Area-weighted means of % TOC 3-3
3-4 Percent of area distribution of % TOC 3-3
3-5 Area-weighted means of water column physical parameters 3-4
XI
-------
4-1 Comparison of Harbor mean sediment concentrations 4-2
4-2 Statistically significant decreases in sub-basin mean 4-2
contaminant sediment concentrations
4-3 Mean sediment concentrations of 2,3,7,8-TCDD and dioxin/furan 4-5
TEQs
5-1 Mean % survival for A. abdita 5-1
6-1 Species richness (total number of species) 6-2
6-2 Means of benthic variables 6-2
6-3 Abundance and biomass means 6-4
6-4 Percent of area within B-IBI categories 6-4
Xll
-------
INTRODUCTION
The New York/New Jersey (NY/NJ) Harbor system has been impacted by over 100 years of
industrial and human population growth. It has a watershed that encompasses over 42,000 km2,
portions of 5 states and a population of over 20 million people. As one of the most heavily
utilized shipping ports on the east coast, it also has considerable refining and manufacturing
industry. Sources of contaminants in the Harbor include municipal and industrial discharges,
atmospheric inputs, non-point source runoff, hazardous waste sites, landfills, combined sewer
overflows and accidental spills. Many of the contaminants present in these sources find their
way into the sediments of the Harbor.
Despite substantial perturbations, the NY/NJ Harbor system still is an essential economic,
recreational, and aesthetic resource. Some commercial fishing for clams, crabs and menhaden
still exists, although it is not as extensive as it was historically. A large recreational fishery still
remains. The Harbor environs are also important resting and feeding areas for migrating birds
and provide habitat for local birds.
To ensure restoration and maintenance of uses of the Harbor, the Harbor Estuary in 1987 was
designated as a National Estuary of Concern. The NY/NJ Harbor Estuary Program (HEP) was
established to provide goals and activities to achieve the objective of maintaining/restoring the
Harbor resources. The New York-New Jersey Harbor Estuary Program (HEP) has prepared a
CCMP or Comprehensive Conservation and Management Plan (U.S. EPA-Region 2, 1996),
which provides goals for the protection and restoration of Harbor resources and actions required
to achieve them. The CCMP includes a section on management of toxic contamination. The
goals of the HEP plan for toxics are:
• To establish and maintain a healthy and productive Harbor/Bight ecosystem, with no
adverse ecological effects due to toxics.
• To ensure that fish, crustaceans and shellfish caught in the Harbor/Bight are safe for
unrestricted human consumption.
• To ensure that dredged sediments in the Harbor are safe for unrestricted ocean disposal.
The current investigation is especially useful to address the first goal of the CCMP toxics
section. In addition, in order to take steps toward attaining all the goals, the HEP plan includes
actions to
1-1
-------
reduce continuing inputs of toxic chemicals to the Harbor and Bight from multiple sources such
as municipal discharges, industrial discharges, combined sewer overflows, storm water
discharges, surface runoff, and atmospheric deposition. Essential to achieving these goals is the
need to estimate with accuracy the status and change in condition of the Harbor resources.
A previous investigation by Adams et al. (1998) provided baseline information for the Harbor.
A probabilistic design allowed sediment toxicity, chemical, and benthic macroinvertebrate data
to be collected for the Harbor and individual sub-basins. The current investigation takes the next
step and begins to assess, with known confidence, whether biological health and sediment
quality are improving, declining or remaining the same. The use of trend assessment has
tremendous utility for managers to evaluate whether management actions are having an
environmental benefit.
OBJECTIVE
This project was designed to support resource management decisions related to pollution control
and remediation throughout the NY/NJ Harbor and to assist the Harbor Estuary Program (HEP)
in evaluating the contaminant monitoring strategy portion of the CCMP for the NY/NJ Harbor
system. This investigation was designed around a primary objective, with two sub-objectives:
Begin Trend Assessment
Estimate with known confidence the percent of area in each of the major sub-
basins of the NY/NJ Harbor system in which the benthic environment is
"degraded", "not degraded", or "not evidently degraded" with respect to benthic
macroinvertebrate assemblages, sediment toxicity, and concentrations of sediment
contaminants; and,
• Evaluate statistically whether the percent of area that is degraded or not degraded
in each of the sub-basins has increased, decreased, or remained the same
compared to the baseline investigation (1993/1994 Sediment Quality of the
NY/NJ Harbor).
ORGANIZATION OF THE REPORT
The purpose of this report is to present summarized data and interpretation to address the three
objectives that were defined at the start of the project. The report has nine chapters. Chapter 1
states the objective of the report. Chapter 2 defines the indicators that were used and how they
1-2
-------
were measured. Chapters 3, 4, 5 and 6 report results from each of the indicator classes, both in
terms of mean condition and percent of area above or below specified threshold values, and
relates these to the baseline investigation 5 years earlier in the Harbor. Chapter 7 provides
discussion of the results in terms of management implications. Chapter 8 contains all references
cited in the report. Several appendices are included: A - sampling station locations and maps; B
- tables of means and % of area exceedances of ERMs for all chemicals measured in the study; C
- lists of pollution-tolerant and pollution-sensitive benthic organisms in the Harbor; and D -
benthic index values for individual stations.
1-3
-------
METHODS
REMAP Region II
New York and New Jersey
Stations -1998
Field and laboratory methods, as well as data
analysis/interpretation procedures used in 1998
were either identical or comparable to methods
used in the 1993/4 baseline investigation of the
Harbor. A more detailed description of methods
can be found in the report from the 1993/4
investigation, Sediment Quality of the NY/NJ
Harbor System (Adams et al., 1998).
STUDY AREA
The New York-New Jersey Harbor, for purposes
of this investigation, includes the lower portions
of the Hudson, Passaic, Harlem, Hackensack and
Raritan rivers, upstream to a near-bottom salinity
of 15 ppt, the East River to Long Island Sound,
and Lower Harbor to the Atlantic Ocean.
The study area was divided into four sub-basins,
based on hydrogeography and similar source
characteristics (Figure 2-1): Upper Harbor,
Newark Bay, Lower Harbor (includes Raritan and
Sandy Hook Bays) and Jamaica Bay. The area of
each sub-basin was determined using Geographic Information System (GIS) ARCInfo software
(Table 2-1).
Raritan
Bay
Sandy Hook Bay
2'L Stations in the study area.
Table 2-1.
Sub-basin
Lower Harbor
Upper Harbor
Jamaica Bay
Newark Bay
Total
Sub-basin
Area %
(km2)
318
104
47
32
501
Areas
of Study
Area
63.5
20.8
9.4
6.4
100
STUDY DESIGN
A stratified random approach was used to
probabilistically select sampling stations. The strata
corresponded to each of four sub-basins where
independent estimates of condition were needed.
Twenty-eight stations were assigned to each sub-basin
(Appendix A). Fourteen stations corresponded to
stations from the 1993/1994 investigation, and 14 were
2-1
-------
chosen specifically for this sampling event. All sites were selected by randomly placing a grid
structure over the study area, selecting grid cells at random from each stratum, and selecting a
random location from within the selected cells. Cells were of equal area within strata. Sampling
was conducted between late July and early September of 1998.
SAMPLING PROCEDURES
The U.S.EPA-Region 2 vessel, R/V CLEAN WATERS, was used for sample collection.
Sampling stations were located using a Global Positioning System (GPS) or Differential-GPS
(D-GPS). Depth of the water column was determined using sonar. Field procedures followed
Reifsteck et al. (1993).
Water Column
A SeaBird model SEE 25 "Sealogger" CTD unit was used to obtain a vertical profile of depth,
dissolved oxygen, pH, temperature, and salinity at each station. Measurements were made from
within a meter of the water surface to approximately a meter above the sediment/water interface.
Water clarity was measured using a 20-cm Secchi disk. Dissolved oxygen, temperature and
salinity at the surface were measured using a Winkler titration, NBS thermometer and a
refractometer, respectively, and compared with the CTD results.
Sediment
A 0.04-m2 stainless steel, Young-modified van Veen grab was used to collect surficial sediment
for chemical analysis and toxicity testing. Multiple grabs were required to collect enough
volume for analysis. Overlying water was carefully drained by allowing suspended floe to settle
for approximately one minute and then carefully suctioning off the overlying water with a clean
section of Tygon® tubing. The top 2 cm of sediment from each grab were removed using clean
stainless steel spoons. A composite of all grabs was homogenized in a clean glass mixing bowl
for 10 minutes. Subsamples were removed for metals, organics, grain size, TOC and toxicity
tests, and transferred to clean sample containers that were stored on ice. The van Veen grab was
rinsed with ambient seawater between grabs at a station and thoroughly cleaned with detergent
and water between stations.
Benthos
Three benthic macroinvertebrate grabs were collected per sampling station using the 0.04-m2
Young-modified van Veen grab. Benthic grabs were alternated with sediment chemistry/toxicity
grabs. Benthic samples were gently washed through a 0.5 mm mesh sieve. The material that
remained was preserved in a 10% buffered formaldehyde-rose bengal solution.
2-2
-------
LABORATORY
METHODS
Standard methods were
used for chemical analyses
(Table 2-2). Individual
chemical parameters are
listed in Table 2-3. PCBs,
pesticides, PAHs, TOC,
grain size, and total
recoverable metals were
analyzed at the U.S.EPA-
Region 2 Laboratory in
Edison, NJ. Total metals,
coplanar PCBs, and
dioxin/furans were
analyzed, under contract to
NOAA, by the
Geochemical and
Environmental Research
Group (GERG) of Texas
A&M University, College
Station, TX. Benthic
macroinvertebrate samples
were processed by Barry
Vittor & Associates, Inc.,
Mobile, AL. Ampelisca
abdita assays were
conducted by the
U.S.EPA-Region2
Bioassay Laboratory in
Edison, NJ and SAIC in Narragansett, RI. An interlaboratory comparison conducted in 1993 and
1994 showed comparable results between these two bioassay laboratories.
All analyses employed appropriate quality assurance samples. Quality assurance goals were
developed and followed for each analysis (Adams, 1998). The quality of the PCB data were
indeterminate at the time of this report; therefore, those data do not appear in this report. For all
other parameters, except for isolated instances, all quality assurance goals were met or exceeded.
The laboratory that conducted the dioxin/furan and total metal analyses participated in the
NOAA Status and Trends Interlaboratory Comparison exercise. Data were entered into two
separate databases and then compared electronically to ensure accuracy in data entry.
Table 2-2. Summary of Physical/Chemical Analytical
Methods
Parameter
PAHs
PCBs*/Pesticides
Major and Trace
Elements
Major and Trace
Elements
Dioxins and
Furans
TOC
Grain size
Method
Methylene chloride extraction;
determination by GC/MS
Methylene chloride extraction;
determination by HRGC/ECD
Total metals: HNO3 and HF acid
digestion: Hg-CVAAS;Cu, Ni,
Pb, Cr, Sb, Sn, As, Se, Ag, Cd-
GFAAS; Al, Fe, Mn, Si, Zn-
FAAS
Total recoverable metals:
HNO3/H2O2 or microwave
digestion: Hg-CVAF;Cu, Ni, Cr,
Ag, Al, Fe, Mn,; Zn-ICP; Pb, Cd,
Se-GFAAS; As, Sb-HYDAAS
Extraction with toluene;
determination by HRGC/HRMS;
second column confirmation for
2,3,7,8-TCDD
Acidification with H3PO4;
determination using a CO2
analyzer
Sieving and pipette analysis
Reference
SW846 3540 and
8270
SW846 3540,
8081/8082;
Lauenstein and
Cantillo, 1993a
Lauenstein and
Cantillo, 1993b
SW846 3015 and
MCAWW 200.7;
Hg - SW846 7471
and MCAWW
245.1
Chambers et al.,
1998
MCAWW 415.1
(U.S. EPA, 1983)
U.S.EPA, 1995
*The quality of the PCB data was indeterminate at the time of this report, so those data do not appear in
this report.
2-3
-------
Table 2-3. Analytical Measurements for Sediment Samples
Polyaromatic Hydrocarbons (PAHs)
Acenaphthene
Acenaphthylene
Anthracene
Benz(a)anthracene
Benzo(b,k)fluoranthene
Benzo(g,h,i)perylene
Benzo(a)pyrene
Benzo(e)pyrene
DDT and its Metabolites
o,p'-DDD
Biphenyl
Chrysene
Dibenz(a,b)anthracene
2,6-Dimethylnaphthalene
Fluoranthene
Fluorene
Ideno( 1,2,3 -c,d)pyrene
2-Methylnaphthalene
1 -Methy Inaphthalene
1 -Methy Iphenanthrene
Naphthalene
Perylene
Phenanthrene
Pyrene
2,3,5-Trimethy Inaphthalene
Chlorinated Pesticides other than DDT
p,p'-DDD
o,p'-DDE
p,p'-DDE
o,p'-DDT
p,p'-DDT
Aldrin
Alpha-Chlordane
Trans-Nonachlor
Dieldrin
Endrin
Heptachlor
Heptachlor epoxide
Hexachlorobenzene
Lindane (y-BHC)
Mirex
Major Elements
Trace Elements
Aluminum
Iron**
Manganese
Silicon
Antimony
Arsenic
Cadmium
Chromium
Lead
Mercury
Nickel
Selenium
Silver
Tin
Zinc
Copper**
PCB Congeners (20)*
No. Congener Name
8 2,4'-dichlorobiphenyl
18 2,2',5-trichlorobiphenyl
28 2,4,4'-trichlorobiphenyl
44 2,2',3,5-tetrachlorobiphenyl
52 2,2',5,5'-tetrachlorobiphenyl
66 2,3',4,4'-tetrachlorobiphenyl
101 2,2',4,5,5'-pentachlorobiphenyl
105 2,3,3',4,4'-pentachlorobiphenyl
110/77 2,3,3',4',6-pentachlorobiphenyl/
3,3 ',4,4'-trichlorotetrabiphenyl
No. Congener Name
118 2,3',4,4',5-pentachlorobiphenyl
126 3,3',4,4',5-pentachlorobiphenyl
128 2,2',3,3',4,4'-hexachlorobiphenyl
138 2,2',3,4,4',5'-hexachlorobiphenyl
153 2,2',3,4,4',5'-hexachlorobiphenyl
170 2,2',4,4',5,5'-hexachlorobiphenyl
180 2,2',3,3',4,4',5-heptachlorobiphenyl
187 2,2',3,4,4',5,5'-heptachlorobiphenyl
195 2,2',3,3',4,4',5,6-octachlorobiphenyl
206 2,2',3,3',4,4',5,5',6-nonachlorobiphenyl
Dioxin and Furan Congeners
2,3,7,8-TCDD
1,2,3,7,8-PeCDD
1,2,3,4,7,8-HxCDD
1,2,3,6,7,8-HxCDD
1,2,3,7,8,9-HxCDD
1,2,3,4,6,7,8-HpCDD
OCDD
2,3,7,8-TCDF
1,2,3,7,8-PeCDF
2,3,4,7,8-PeCDF
1,2,3,4,7,8-HxCDF
1,2,3,7,8,9-HxCDF
2,3,4,6,7,8-HxCDF
1,2,3,4,6,7,8-HpCDF
1,2,3,4,7,8,9-HpCDF
OCDF
Other Measurements
Grain Size
TOC
* The quality of the PCB data was indeterminate at the time of this report; therefore, those data do not appear in this
report.
** Results are total recoverable values versus total values for other metals.
2-4
-------
Major and Trace Elements
Sediment samples were prepared for bulk metals analyses using two procedures: 1) digestion
with nitric and hydrofluoric acids (total metals); and 2) digestion with nitric acid (total
recoverable metals). Total analysis was done to provide comparability with the USEPA-Office
of Research and Development (ORD) National Coastal Assessment (NCA) and with the database
used to develop ERLs and ERMs (Long et al, 1995). Total recoverable analysis provided the
possibility for comparison to historical data. Subsequent data analyses are based on total metals
results, except for aluminum, copper, iron, manganese, and selenium. Mercury was analyzed by
cold vapor atomic absorption (CVAA). Copper, nickel, lead, chromium, hexavalent chromium,
antimony, tin, arsenic, selenium, silver and cadmium were analyzed by graphite furnace atomic
absorption spectroscopy (GFAAS). Other metals (aluminum, iron, manganese, silicon and zinc)
were determined by flame atomic absorption spectroscopy (FAAS). Metal concentrations are
reported on a dry weight basis. The sediment Standard Reference Material (SRM) used was
National Research Council of Canada (NRCC) MESS2.
Organic Compounds
For analysis of pesticides and PCBs, aliquots of sediment were dried and extracted. The
chlorinated pesticides and PCBs were quantified using high resolution capillary gas
chromatography with electron capture detection (GC/ECD). The data are reported in ng/g dry
weight. The sediment SRM used with these samples was National Institute of Technology
(NIST) 1941a. The PCB data do not appear in this report because of QA concerns.
Twenty-two poly cyclic aromatic hydrocarbons (PAHs) were measured (U.S.EPA, 1998).
Aliquots of sediment were dried and extracted. Gas chromatography/mass spectrometry
(GC/MS) was used for analysis. Results are reported as ug/kg, dry weight. The SRMs used
were NIST 194la.
Analysis of sediments for seventeen dioxin and furan congeners was completed using a method
developed by NOAA (Chambers et al., 1998). Frozen sediment samples were thawed and
centrifuged to remove excess water. Approximately 10 g of sediment were used for
determination of percent solids. Another 10 g were combined with quartz sand for extraction.
The extracts were analyzed by high resolution gas chromatography/high resolution mass
spectrometry (HRGC/HRMS).
Sediment Physical Parameters
Grain size analysis was conducted according to U.S.EPA (1995), except samples were not
digested with hydrogen peroxide. Sand was defined as the fraction that was retained on a 63-u
sieve. Percent silt and percent clay were determined using pipette analysis of the filtrate.
Percent moisture was obtained by accurately weighing 10 g of sediment, drying overnight at
105°C and
2-5
-------
reweighing. The total organic carbon (TOC) method was based on the U.S.EPA method
MCAWW 415.1 (U.S.EPA, 1983). The laboratory control sediment was BCSS Marine
Sediment.
Toxicity Methods
Ampelisca abdita Assays
Ten-day acute, static, non-renewal sediment toxicity tests were conducted using the amphipod,
Ampelisca abdita (ASTM, 1993). Batches of A. abdita were supplied by East Coast Amphipod
of Kingston, Rhode Island. The amphipods and control sediment were collected from the
Narrow River, Rhode Island and the U.S. Army Corps of Engineers' Long Island Sound (LIS)
reference station. Control sediment was press-sieved through a 0.5-mm mesh stainless steel
sieve to remove resident amphipods and debris. Test sediment was press-sieved through a 2.0
mm stainless steel sieve to remove large debris and predaceous organisms. If amphipods were
present, the test sediments were press-sieved through a 1.0 mm stainless steel sieve. For each
toxicity test, 200 ml of composited, press-sieved sample were placed in 1 L glass test chambers
and covered with 600 ml of seawater. Five replicate test chambers were used for each sample.
Each replicate contained 20 organisms.
Post-test enumeration of amphipods was performed without knowledge of sample identity to
prevent bias. If less than 20 amphipods were found, the test sediment was stored in the dark for
up to 48 hours to encourage emergence of any remaining amphipods. Final organism counts
were confirmed by a second scientist. Minimum control survival for satisfying test performance
criteria was 90%. Sodium dodecyl sulfate (SDS) was used as a reference toxicant to evaluate the
sensitivity of each batch of amphipods. Reference toxicant results were all within the acceptable
range for this species.
Benthic Macro in vertebrate Assemblages
Three replicate grabs for benthic macroinvertebrate community structure were obtained at each
station. The grabs were processed by being washed through a 0.5 mm screen on-board the
sampling vessel. Invertebrates from two of the replicates were sorted and identified, the third
replicate was archived. Procedures for sorting, identifying, and measuring the biomass of
benthic macroinvertebrates followed EMAP procedures (U.S. EPA, 1995; Frithsen et al., 1994).
Sample processing, as well as species identifications, enumerations and biomass measurements
were done by Barry Vittor & Associates, Inc. (Mobile, AL). The macrobenthos were identified
to the lowest practical taxonomic category. Rare or previously undocumented specimens from
the Harbor were put aside in a specimen voucher collection. A minimum of 10% of all samples
were resorted by a different technician. Ten percent of all samples were also subjected to a
second identification and enumeration by a different taxonomist.
2-6
-------
Organisms were grouped by taxa for biomass determination. To standardize the biomass
measurements, all samples were preserved in a 10% solution of buffered formaldehyde for at
least two months before the biomass measurement. Hard-bodied organisms (bivalves <2 cm and
gastropods) were acidified in 10% HCL until all visible traces of shell material were removed.
Bivalves larger than 2 cm were shucked before determination of biomass. Biomass was
determined as dry weight after drying for at least 48 hours at 60°C.
DATA ANALYSIS
Chemical Data
For several classes of compounds, data analyses were performed on summed results. Total
PAHs were the sum of the concentrations of the 23 individual PAHs. Total chlordane was the
sum of the concentrations of heptachlor, heptachlor-epoxide, oxychlordane, gamma-chlordane,
alpha-chlordane, trans-nonachlor and cis-nonachlor. Non-detects were not included in the
calculation of total concentrations.
Data analyses for metals were based on total metals results, except for aluminum, copper, iron,
manganese and selenium which are total recoverable.
Toxicity Data
Amphipod survival data were not transformed, since an examination of a large historical data set
from S AIC has shown that A. abdita percentage survival data meet the requirement of normality
(Thursby et al., 1997).
Benthic Macro in vertebrate Data
Benthic macroinvertebrate data from the
two replicates were averaged and used
in subsequent analyses. Nine individual
measures and one composite index
(benthic index of biotic integrity or B-
IBI) were used to evaluate the condition
of benthic assemblages in the study
area. Diversity was evaluated by using
species richness (number of species)
and the Shannon-Wiener diversity index
(Shannon and Weaver, 1949).
A multi-metric benthic index of biotic
Table 2-4. Benthic Macroinvertebrate
Measures Included in B-IBI
Abundance and
Biomass
Abundance (#/m2)
Biomass (g/m2)
Species Composition
Abundance of pollution-
indicative taxa (%)
Abundance of pollution-
sensitive taxa (%)
Species Diversity
Number of Taxa (#)
2-7
-------
integrity (B-IBI) was developed for the NY/NJ Harbor (Adams et al., 1998). The B-IBI
incorporated the five benthic macroinvertebrate metrics (Table 2-4) into a single value that
described the condition of the benthos. These five metrics were those which most effectively
distinguished normal sites from all others. The metrics were evaluated for two salinity regimes
(polyhaline and euhaline) and two sediment types (mud and sand), and threshold values were
defined for each.
The index was calculated by scoring each selected metric as 5, 3, or 1 depending on whether its
value at a site approximated, deviated slightly from, or deviated greatly from conditions at the
best reference sites. The B-IBI value for each station is calculated as the mean score of the five
metrics. A mean score of 5 indicated that the site was approximately equivalent to the best
reference sites. A score of 3 or 1 indicated that
B-IBI score
1
Interpretation
Similar to reference
Very different from reference
the site slightly deviated or greatly deviated
from conditions at the best reference sites and
ci-t-i j-«- f f would be considered to have impacted benthos.
Slightly different from reference r*u ™ T^T
The overall validation efficiency of the B-IBI
was 93%.
The EMAP-VP benthic index, which was developed for the east coast of the U.S. from Cape Cod
to the mouth of Chesapeake Bay, was also applied. The three measures that are incorporated
into this index are: salinity-normalized Gleason's D for infaunal and epifaunal species, salinity-
normalized expected number of tubificids, and abundance of spionids (Strobel et al., 1995). This
index had a classification efficiency of approximately 90% on a test data set.
Condition Estimates
Two types of characterizations were produced for this investigation. The condition of each
stratum and the Harbor as a whole were assessed in two ways: 1) mean condition; and 2) percent
of area exceeding threshold (or critical) values for selected parameters. The spatial distribution
of degraded and non-degraded stations was also evaluated using a Geographic Information
System (GIS) display of individual station results. Individual sub-basins were separately
characterized for each parameter, resulting in four characterizations. An additional
characterization, the "Harbor", combines all four of the sub-basins that are commonly known as
the Harbor proper (i.e., Jamaica Bay, Newark Bay, Lower Harbor and Upper Harbor).
Mean Condition
Since the sampling stations within each stratum or sub-basin were selected with equal inclusion
probabilities, the mean parameter values for a stratum, h, and its variance were calculated as:
yh= = — (i)
1=1 n
2-8
-------
where
yih was the variable of interest (e.g., concentration of mercury), and
nh was the number of samples collected from stratum h.
The weighted mean value for L strata with combined area^4 is given by
where the weighting factors, Wh = Ah/A, ensure that each stratum h is weighted by its fraction of
the combined area for all L strata. An estimator for the variance of the stratified mean (3) is
V(yst)= E Wh2Var(yh) (4)
Strata were combined to develop estimates for the study area as a whole and for the New
York/New Jersey Harbor, following Holt and Smith (1979). Confidence intervals were
calculated as 1.64 times the standard error, where the standard error was the square root of the
variance.
T-test comparisons were made for samples collected in 1993 and in 1998 to evaluate whether
they were significantly different. Single variables (e.g. silver) were compared between years for
the Harbor estimates and the sub-basin estimates using SAS v6.12 software package (SAS,
1989). Options within the SAS software allow t-test comparisons of data which have either equal
or unequal variances. The first step was to determine whether the data had equal variances.
When the variances of the two years of data were equal, they were compared using the Cochran
and Cox approximation of the t statistic, and when unequal, they were compared using the
Satterthwaite approximation.
2-9
-------
Percent of Area Estimates
Estimates of percent of area exceeding selected thresholds (e.g., mercury concentration greater
than ERM) were calculated asp = B/n, where B was number of samples exceeding the threshold
and n was the total number of samples in the stratum. For strata with equal inclusion probability,
the exact confidence intervals forp were calculated from the binomial distribution using the
formula of Hollander and Wolfe (1973). Below detection limit values were included as zero for
percent of area estimates.
The confidence interval for combined strata was calculated using the normal approximation to
the binomial, with the 90% confidence interval of stratified estimates of proportions,/^,,
estimated as:
where
L
Pst = E
h= 1
SELECTION OF THRESHOLD VALUES
To conduct the data analyses needed to produce percent of area estimates, threshold values or
"levels of concern" were required. The threshold values used were either established by
regulation or Agency guidance (e.g., Ampelisca abdita toxicity), were screening guidelines (e.g.,
contaminant ERLs and ERMs) or were developed based on previous investigations (e.g., B-IBI
and EMAP benthic index).
Physical Data
For grain size, a value of 40% silt-clay was used to distinguish between sand (<40% silt-clay)
and mud (>40% silt-clay) substrate. This cut-off was established using cluster analysis on
Environmental Monitoring and Assessment Program (EMAP) data from 525 randomly selected
sites, sampled between 1990 and 1993 in the Virginian Province.
Chemical Data
For determination of potential biological effects, this study's chemical data, except dioxins and
furans, were evaluated using the effects-based guidelines (Table 2-5) of Long and Morgan
(1991)
2-10
-------
Table 2-5 ERL and ERM Concentrations for Sediment Trace
Compounds (Long and Morgan, 1991; Long et al.,
Chemical Analyte
Trace Elements (ppm)
Antimony
Arsenic
Cadmium
Chromium
Copper
Lead
Mercury
Nickel
Silver
Zinc
DDT and Metabolites (ppb)
DDT
ODD
p,p'-DDE
DDE
Total DDT
Other Pesticides (ppb)
Chlordane
Dieldrin
Endrin
Polynuclear Aromatic Hydrocarbons (ppb)
Acenaphthene
Acenaphthylene
Anthracene
Benzo(a)anthracene
Benzo(a)pyrene
Chrysene
Dibenz(a,h)anthracene
Fluoranthene
Fluorene
2-Methylnaphthalene
Naphthalene
Phenanthrene
Low molecular weight PAHs
High molecular weight PAHs
Pyrene
Total PAH
ERL Concentration
2
8.2
1.2
81
34
46.7
0.15
20.9
1
150
1
2
2.2
2
1.58
0.5
0.02
0.02
16
44
85.3
261
430
384
63.4
600
19
70
160
240
552
1700
665
4022
Metals and Organic
1995).
ERM Concentration
25
70
9.6
370
270
218
0.71
51.6
3.7
410
7
20
27
15
46.1
6
8
45
500
640
1100
1600
1600
2800
260
5100
540
670
2100
1500
3160
9600
2600
44792
2-11
-------
and Long et al. (1995). This approach utilizes data from laboratory spiked bioassays,
equilibrium partitioning models, and synoptic chemical and biological data from field surveys.
Ranges of chemical concentrations are determined that are usually associated with biological
effects (Effects Range-Median or ERM), and at which biological effects begin to be seen
(Effects Range-Low or ERL). New York State has adopted some of these ERLs and ERMs for
Sediment Guidance Criteria (NYSDEC, 1999). The Long and Morgan (1991) and Long et al.
(1995) values were used because they include thresholds for most of the chemicals that were
measured, allowing this study to provide an integrated contaminant response. Consensus-based
sediment quality guidelines for PAHs (Swartz, 1999) were also evaluated. Additional alternative
thresholds and evaluation methods, such as proposed sediment quality criteria (U.S.EPA, 1994),
SEM-AVS (DiToro et al., 1990; NOAA, 1995), and aluminum normalization, were applied in
the 1993/4 investigation (Adams et al., 1998) but were not repeated for the current investigation.
Concentrations of 17 dioxin and furan congeners also were measured in sediments. Sediments
that are contaminated with dioxins and furans contain a complex mixture of congeners.
Individual congeners differ greatly in their toxicity and carcinogenicity and, although specific
individual congeners may not be present in concentrations of concern, the combined effect of
existing concentrations may be toxicity. A "toxicity equivalency factor (TEF)" was applied to
each congener, then summed across all dioxin and furan congeners to give "toxicity equivalents
(TEQ)". TEFs permit estimation of total dioxin/furan toxicity, expressed as an equivalent
amount of 2,3,7,8-TCDD. Previously only TEFs to address human toxicity had been developed
(U.S.EPA, 1989; Cura et al., 1995). Recently, however, TEFs were proposed that could be used
to calculate toxic effects of dioxins and furans on fish and wildlife (U.S.EPA, 2001).
Sediment Toxicity Data
Significant toxicity for the amphipod, A. abdita, was defined as survival less than or equal to
80% of the mean control survival and statistically different (p<0.05) from controls
(U.S.EPA/U.S. ACE, 1991).
Benthic Index
Threshold values for each measure (metric) in the NY/NJ Harbor Benthic Index of Biotic
Integrity (B-IBI) were established based on the distribution of its values at reference sites.
Similar to the Index of Biotic Integrity (IBI) approach (Kerans and Karr, 1994), each measure
was scored as 5, 3, or 1 based on whether its value at a site approximated, deviated slightly from,
or deviated greatly from conditions at the best reference sites. Threshold values were established
at the 5th and 50th (median) values for reference sites in each habitat. Metric values below the
5th percentile compared to the reference sites were scored as a 1; values between the 5th and
50th percentile were scored as a 3; and values above the 50th percentile were scored as a 5. An
index value for a location was calculated by taking the mean of the scores for the individual
measures at a location. If the mean of all the benthic index metrics at a location was less than or
equal to 3, the location was considered to have impacted benthos.
2-12
-------
PHYSICAL
PARAMETERS
Physical measurements of sediment and water matrices provide information useful to the
interpretation of chemical and biological data, as well as understanding of the natural conditions
of the Harbor. Physical characteristics of the sediments included grain size (as % silt-clay) and
total organic carbon (TOC) content. Water parameters, including water column depth,
temperature, salinity, and dissolved oxygen, were measured at each sampling location using a
single CTD profile.
Depth
The mean depth for the entire Harbor was 8.0 m. Mean depths were similar for all Harbor sub-
basins, except the Upper Harbor (Table 3-1). The Upper Harbor mean at 10.8 m, was 2-3 m
deeper than other sub-basins.
The mean depth for the Harbor is significantly different between 1993/1994 and 1998. The
mean was 1.5 m higher in 1998. This may be due to additional dredging that took place between
the investigations. Portions of the Harbor are dredged to maintain shipping channels. The mean
depths of the individual sub-basins are statistically similar to the 1993/1994 investigation.
Table 3-1. Area-Weighted Means for Depth
Depth (m)
(± 90% C.I.)
Harbor
8.0
±1.4
Jamaica
Bay
7.6
±1.1
Newark
Bay
9.0
±1.3
Lower
Harbor
7.0
±1.7
Upper
Harbor
10.8
±1.8
Percent Silt-Clay
Average percent silt-clay in sediments of the entire Harbor was 34.3%. Mean percent silt-clay
varied among sub-basins (Table 3-2). Lower Harbor was the sandiest with only 27% silt-clay.
Upper Harbor and Newark Bay were the muddiest sub-basins with 50.4% and 46.9% silt-clay,
respectively.
3-1
-------
The mean percent silt-clay is nearly identical
for the Harbor from 1993/4 to 1998. The
sub-basins also were similar, except for
Newark Bay, which was significantly
different in 1998 (46.9%) versus 1993/4
(68.1%). Overall, variability in percent silt-
clay values appeared to be lower in 1998
than in 1993/4.
A sub-basin pattern similar to the average
silt-clay results was also apparent when
results are expressed as areal extent (Figure
3-1). In terms of spatial extent, 43% of the
Harbor is predominantly mud (>40% silt-
clay). Sixty-one percent of Newark Bay was
comprised of mud compared to 32% of
Lower Harbor, 50% of Jamaica Bay and
68% of Upper Harbor.
The percent of area estimates between
D Sand ( 40%)
o
•I-*
c
-------
Table 3-3 Area-Weighted Means of % TOC
% TOC, dry wt.
(± 90% C.I.)
Harbor
2.3
±0.8
Jamaica
Bay
2.6
±0.7
Newark
Bay
2.5
±0.4
Lower
Harbor
1.7
±0.5
Upper
Harbor
3.8
±0.7
When TOC was examined on an areal basis (Table 3-4), the sub-basins were very similar, with
Upper Harbor and Newark Bay having similar and considerable percent of area with TOC
exceeding 1.5%.
Table 3-4 Percent of Area Distribution of % TOC ( 90% C.I.)
< 0.5%
0.5 to 3.5%
Harbor
24.8
±4.0
24.1
±4.1
8.8
±2.8
10.3
±3.2
32.1
±4.1
Jamaica
Bay
39.3
±15.1
3.6
±5.8
10.7
±9.6
7.1
±8.0
39.3
±15.1
Newark
Bay
0
17.9
±11.9
39.3
±15.1
21.4
±12.7
21.4
±12.7
Lower
Harbor
32.1
±14.5
32.1
±14.5
3.6
±5.8
7.1
±8.0
25.0
±13.4
Upper
Harbor
3.6
±5.8
10.7
±9.6
14.3
±10.9
17.9
±11.9
53.6
±15.5
There were no sites in Newark Bay where TOC was less than 0.5%, whereas Jamaica Bay and
the Lower Harbor had a third of their areas
with TOC less than 0.5%. Highly organically-
enriched areas ranged from 21.4% of Newark
Bay to 53.6% of Upper Harbor.
The percent of area distribution of TOC in
1998 was similar to 1993/4 for the Harbor
(Figure 3-2). A significant shift was seen
between the three categories of TOC greater
than 1.5%. This also may be attributed to the
effect of dredging. Individual sub-basins also
were similar between 1993/4 and 1998,
• >/= 3.5%
D 2.5 to
-------
although there was some shifting between the intermediate TOC categories.
Water Column Profile
Mean bottom water temperature during the sampling period was similar in all the sub-basins
(Table 3-5). Means ranged from 21.0°C in Lower Harbor to 24.3°C in Newark Bay. Mean
bottom water temperature for the entire Harbor was 21.7°C. For the Harbor overall, there was
no significant difference in mean bottom temperature between 1993/4 and 1998.
Table 3-5. Area-Weighted Means of Water Column Physical Parameters
Bottom Temp. (°C)
(± 90% C.I.)
Bottom Salinity (ppt)
(± 90% C.I.)
Bottom D.O. (mg/1)
(± 90% C.I.)
Harbor
21.7
±1.1
24.8
±1.0
7.0
±0.8
Jamaica
Bay
24.1
±0.4
27.2
±0.3
6.5
±0.9
Newark
Bay
24.3
±0.6
21.1
±0.6
5.4
±0.4
Lower
Harbor
21.0
±1.1
25.8
±0.7
7.7
±0.6
Upper
Harbor
22.2
±1.0
22.0
±2.0
5.7
±0.6
Mean bottom salinity for the entire Harbor was 24.8 ppt. Newark Bay and Upper Harbor were
significantly lower (p<0.01) than the other two systems. The lowest salinity value measured
during the study was 5.6 ppt in the Hudson River; all other values exceeded 12 ppt. There was a
slight difference in Harbor mean bottom salinity between 1993/4 (26.2± 0.4) and 1998, with
1998 being lower.
Dissolved oxygen concentrations are typically highly variable both temporally and spatially, and
NY/NJ Harbor is no exception. This study obtained a single measurement of dissolved oxygen
at each station. New York City DEP has a more spatially and temporally complete dissolved
oxygen data set for 1998 (NYCDEP, 1999). It should be noted that, although mean D.O. values
did not fall into a category of impaired, this may not be the case at individual stations. Each sub-
basin had stations with D.O. measurements that were below 3 mg/1.
3-4
-------
SEDIMENT
CHEMISTRY
The direct measurement of the concentration and kind of chemicals present in sediment provides
insight into the ecological effects that might be present, as well as suggesting possible sources of
contaminants. However, there needs to be an interpretative step to "translate" those chemical
data into indication of ecological impact.
This investigation used the aquatic effects-based guidelines of Long and Morgan (1991) and
Long et al. (1995) to evaluate the chemical data (except for dioxins and furans). This approach
utilizes data from laboratory spiked bioassays, equilibrium partitioning models and synoptic
chemical and biological data from field surveys. Two concentrations are determined for each
chemical that are associated with incidence of biological effects in the data set that was used for
development. The Effects Range-Low (ERL) value is the concentration at which adverse
biological effects begin to be seen, and the Effects Range-Median (ERM) concentration is that
usually associated with adverse biological effects. New York State has adopted some of the
ERLs and ERMs for Sediment Guidance Criteria (NYSDEC, 1999). The ERM and ERL values
were used because they include thresholds for most of the chemicals that were measured,
allowing this study to provide an integrated contaminant response.
Concentrations of 17 dioxin and furan congeners also were measured in sediments of the study
area. Individual congeners differ greatly in their toxicity and, although individual congeners may
not be present in concentrations of concern, their combined concentrations may be toxic. A
"toxicity equivalency factor (TEF)" was applied to each congener, then summed across all
dioxin and furan congeners to give "toxicity equivalents (TEQ)". TEFs permit estimation of
total dioxin/furan toxicity, expressed as an equivalent amount of 2,3,7,8-TCDD.
Mean Condition
Chemical contamination is pervasive in the Harbor. The mean values for 7 of 10 trace elements
for which ERL and ERM thresholds exist were at or above ERL levels (Appendix B). Cadmium,
and antimony were the only ERLs not exceeded, and chromium was present at a mean
concentration equal to the ERL. The Harbor mean for mercury exceeded the ERM value. With
regard to organic chemical contaminants, the ERL value was exceeded for the Harbor mean
concentrations of total chlordane, total DDT, DDT, total PAHs and high molecular weight
PAHs, as well as several of the individual PAHs. The ERM value was exceeded for DDT.
4-1
-------
Table 4-1. Comparison of Harbor Mean Sediment
Concentrations (± 90% C.I.).
Mercury
(ppm)
Silver
(ppm)
Total Chlordane
(ppb)
Total DDT
(ppb)
Total PAHs
(ppb)
1993/4
0.74
±0.14
1.59
±0.30
5.11
±1.01
31.59
±16.64
7177.4
±2607.9
1998
0.86
±0.54
1.57
±0.74
0.64
±0.70
20.87
±2.12
5327.08
±47.55
statistical
difference
(p<0.10)
• "(93/94
higher)
A comparison of 1993/4 and 1998
shows that, among the major groups
of contaminants, the Harbor mean
for total chlordane experienced a
statistically significant decrease in
the five years from 1993/4 to 1998
(Table 4-1). Mean values for most
other individual contaminants in the
Harbor decreased only slightly
during that time period, if at all
(Appendix B).
Concentrations of some sediment
contaminants in the individual sub-
basins decreased enough to be
statistically significant (Table 4-2).
Total chlordane decreased in all the
sub-basins except Upper Harbor.
Significant decreases also were
seen for silver in Newark Bay as well as for total DDT in Upper Harbor.
Of the Harbor sub-basins, Newark
Bay had the highest average
concentration of all the metals
measured, except for silver,
manganese and aluminum, which
were higher in Upper Harbor
(Appendix B). Upper Harbor had
the highest mean concentrations
of total chlordane and total PAHs,
as*well as for most of the
individual PAHs, except for 2,6-
dimethylnaphthalene which was
highest in Jamaica Bay. Newark Bay had a mean concentration of parent DDT that was 200
times higher and a mean total DDT that was 50 times higher than the next highest sub-basin.
Table 4-2. Statistically Significant Decreases in Sub-
basin Mean Contaminant Sediment Concentrations
(p<0.10)
Silver
Total Chlordane
Jamaica
Bay
•
Newark
Bay
• •
•
Lower
Harbor
•
Upper
Harbor
•
Areal Extent
Chemical contamination was present throughout the Harbor. When expressed on an area basis,
86% (± 4) of the Harbor exceeded an ERL concentration for at least one contaminant, and 45%
(±4) of the Harbor exceeded an ERM concentration for at least one contaminant (Figure 4-1).
This is very similar to conditions measured in 1993/4.
4-2
-------
Estimates of the percent of area in the Harbor that exceeded an ERL and/or ERM for any metal,
pesticide, and PAH showed that all contaminant groups appeared to contribute to Harbor
contamination (Figure 4-1). In 1998, while the extent of metals contamination remained
constant, pesticide levels have declined from 1993/4.
Evaluation of the individual chemicals showed that mercury was the most ubiquitous chemical.
Sixty-eight percent (± 4) of the area of the Harbor exceeded the ERL and 42% (± 4) exceeded
the ERM for mercury (Figure 4-2). Between
1993/4 and 1998 metals levels have remained
approximately the same. The area of the Harbor
affected by low-level cadmium contamination _
has significantly decreased. f
Organic contaminants above ERL values
affected between <1% to 47% of the Harbor.
Total DDT, high molecular weight PAHs, and
several individual PAHs had the highest percent
of areas above ERLs. The percent of area above
organic ERMs was low, ranging from <1% to
8%. In 1993/4, organic contaminants above
ERL values affected from 56% to 83% of the
Harbor area, and chlordane resulted in the
greatest percent area (32%) of an organic
contaminant above an ERM (Figure 4-3).
l > ERL l~l > ERM
Any chemical Any pesticide Total PCBs
Any metal Any PAH
Figure 4-1. Percent of area exceeding ERLs and
ERMs for individual chemical groups in 1993/4 (1st
bar) and 1998 (2nd bar). (Quality of 1998 PCB data
were indeterminate at time of publication.)
Figure 4-2. Percent of area greater than ERL and
ERM values for 1993/4 (1st bar) and 1998 (2nd bar)
for metals in the Harbor. (Total copper was not
analyzed in 1998.)
Total DDT HMW PAHs
Total PAHs Total chlordane
Figure 4-3. Percent of Harbor area greater than
ERL and ERM values for 1993/4 (1st bar) and 1998
(2nd bar) for organics in the Harbor.
4-3
-------
Within the Harbor, Newark Bay and the Upper Harbor had the most widespread and diverse
contaminant problems, with 96% (± 6) and 82% (± 12) of their areas exceeding an ERM value
for at least one chemical (Figure 4-4). These two sub-basins, at 100% and 93% (± 8), also had
the highest percent of area exceeding at least five ERLs. The entire Harbor exceeded five or
more ERLs at 60% (± 4) of its area. Approximately 8% (± 1) of the Harbor exceeded at least 5
ERMs with Newark Bay having 50% (± 16) and UH 25% (± 13) exceedances in 1998. Jamaica
Bay and Lower Harbor had no stations with 5 or more ERMs exceeded.
Mercury had the highest percent area of all the metals exceeding an ERM in the Harbor (42%).
Focusing on mercury in each of the sub-basins showed that in 1998, 96% of the area in Newark
Bay and 71% of the area in the Upper Harbor exceeded the ERM concentration (Figure 4-4).
One hundred percent of Newark Bay and 96% of the Upper Harbor exceeded the ERL for
mercury. This is compared to 100% and 93%, respectively, in 1993/4.
Mercury
n Below ERL: < 0.15 ppm
O Between ERL and ERM: 0.15 to 0.71 ppm
A Above ERM: > 0.71 ppm
NEW
JERSEY
Sandy Hook Bay
Total PAHs
O Below ERL: < 4022 ppb
O Between ERL and ERM: 4022 to 44,792 ppb
A Above ERM: > 44,792 ppb
NEW
JERSEY
Sandy Hook Bay
Figure 4-5. Distribution of mercury
concentrations in 1998 by station.
Figure 4-6. Distribution of total PAH
concentrations in 1998 by station.
4-4
-------
It was possible to distinguish some general patterns of chemical distribution in sediments. The
pattern of mercury distribution in the Harbor may indicate that a possible source or sources exist
in or above Newark Bay and Upper Harbor (Figures 4-5). Concentrations were elevated down
the Arthur Kill across Raritan Bay to Sandy Hook Bay, following the circulation pattern for this
part of the Harbor. Total PAHs exhibited a similar pattern (Figure 4-6). These observations are
similar to those from 1993/4.
Dioxins and Furans
Concentrations of seventeen
congeners of dioxins and furans
were measured at each station in
Newark Bay, Jamaica Bay, Lower
Harbor, and Upper Harbor. Most
sediments, if contaminated with
dioxins and furans, have them
present as complex mixtures.
Although individual congeners
may not be present in
concentrations of concern, their
combined concentrations may be
toxic. A "toxicity equivalency
factor" has been quantified for
each congener, allowing
estimation of total dioxin/furan
toxicity in fish and birds,
expressed as "toxicity equivalents"
orTEQs(U.S.EPA, 2001).
Table 4-3. Mean Sediment Concentrations of
2,3,7,8-TCDD and dioxin/furan TEQs (± 90%
confidence limits)
Harbor
Jamaica
Bay
Lower
Harbor
Upper
Harbor
Newark
Bay
2,3,7,8-TCDD
(ng/kg, dry wt.)
1993/4
_
4.0
±2.6
7.5
±3.4
5.5
±1.8
not
analyzed
1998
6.5
±1.6
1.6
±0.9
3.0
±1.7
6.4
±2.7
49.0
±24.6
TEQs
(fish)
1998
9.7
±2.0
2.5
±1.2
5.0
±2.8
12.4
±3.7
57.1
±26.7
TEQs
(birds)
1998
22.5
±3.1
12.3
±5.0
15.1
±7.4
32.5
±9.1
78.1
±31.9
Low levels of dioxins and furans
were found in all sub-basins. The mean concentration of the most toxic dioxin congener,
2,3,7,8-TCDD, was highest in Newark Bay (Table 4-3), with concentrations in the other sub-
basins substantially lower but similar to one another. Incorporating all congeners into the
calculation of TEQs also resulted in the Newark Bay having a significantly higher mean of
2,3,7,8-TCDD equivalents than the other three sub-basins.
Comparison of 2,3,7,8-TCDD levels in 1993/4 and 1998 show that, while levels in some sub-
basins appear to be declining, these changes are not statistically significant.
4-5
-------
SEDIMENT TOXICITY
Sediment toxicity tests, which involve the exposure of organisms to sediments in a laboratory
setting, are useful because they provide a direct indication of the effects of sediment
contaminants. Because the tests are done in a laboratory, confounding factors such as
temperature, salinity, and dissolved oxygen can be controlled. Toxicity tests also integrate the
effects of complex mixtures of chemicals in sediment, including chemicals that were not
measured. However, two disadvantages of toxicity tests are that individual species of test
organisms can vary in their sensitivity to chemicals, and the relevance of toxicity test results to
field conditions is difficult to establish. For these reasons, toxicity tests are best used as in
conjunction with sediment chemistry and some measure of in situ biological response (e.g.,
benthic macroinvertebrate community structure).
This investigation used survival of the amphipod,
Ampelisca abdita, to indicate sediment toxicity.
Sediments at a station were considered toxic using the
Ampelisca abdita toxicity test if percent survival was less
than 80% compared to controls. These criteria are similar
to those in U.S.EPA/U.S.ACE (1991). Sediments were
considered "highly toxic" if A. abdita survival was less
than 60% compared to survival in control sediments.
Mean Condition
Mean percent survival of Ampelisca abdita (as percent of
control survival) for 1998 was fairly high for the Harbor
overall (Table 5-1). Mean survival was comparable
within each sub-basin of the Harbor except Newark Bay
where it was significantly less than the Harbor as a whole.
Lower Harbor exhibited the highest mean survival.
Table 5-1. Mean %
Survival for A. abdita*
(± 90% C.I.)
Harbor
Jamaica
Bay
Newark
Bay
Lower
Harbor
Upper
Harbor
1993/4
87.9
±4.1
84.9
±7.7
66.5
±15.1
91.0
±5.9
86.6
±6.3
1998
89.8
±2.8
77.0
±9.9
63.7
±10.7
96.0
±5.9
84.5
±10.0
! Adjusted for control survival.
A comparison between the investigations of 1993/4 and
1998 shows that mean percent survival was very similar
for the Harbor and across the sub-basins. There were no statistically significant changes.
5-1
-------
Areal Extent
In 1998, out of a total area of 501 km2,
approximately 60 km2 (12%) of the
Harbor proper was toxic to A. abdita and
48 km2 of that (9.5% of the total area) was
highly toxic (Figure 5-1). Newark Bay
and Jamaica Bay have more widespread
toxic sediments (50 and 32%,
respectively) than the rest of the Harbor.
Newark Bay also has a larger percent area
of highly toxic sediments (36%) than other
Harbor sub-basins. Although relatively
large percentages of Newark and Jamaica
Bay sediments were toxic, these were the
smallest Harbor sub-basins. The
total toxic area of these sub-basins (31
km2) was !/2 of the acreage of toxic
sediments in the entire Harbor.
D toxic (60-80% survival)
100
highly toxic (<60% survival
CD
CD
Q_
Figure 5-1. Percent of area withAmpelisca toxicity.
Amphipod Toxicity
D Non-Toxic: > 80% of control response (survival)
O Toxic: 60 to 80% of control response (survival)
A Highly Toxic: < 60% of control response (survival)
NEW
JERSEY
Raritan
Bay
Sandy Hook Bay
Individual stations toxic to A. abdita were
scattered around the Newark Bay, Upper
Harbor and Jamaica Bay sub-basins (Figure 5-
2). Highly toxic stations were concentrated in
the Arthur Kill (Newark Bay sub-basin) and
throughout Jamaica Bay. The Upper Harbor
had two stations on the western Long Island
Sound side of the East River with highly toxic
sediments. The one station in the Lower
Harbor that exhibited toxicity was near the
entrance to Jamaica Bay.
Comparing 1998 with 1993/4 shows that the
overall prevalence (Figure 5-1) and
distribution of toxicity in the Harbor remains
similar. Overall, the Harbor extent of toxicity
was identical between 1993/4 and 1998. There
also were no sub-basins with statistically
significant changes in the extent of toxicity.
Figure 5-2. Distribution of stations with A. abdita toxicity.
5-2
-------
Individual stations with measurable toxicity varied slightly between 1993/4 and 1998 (Figure 5-
2). The lower Passaic River and Arthur Kill still had many toxic and highly toxic stations. The
Lower Harbor still had the least number of toxic stations.
5-3
-------
BENTHIC
MACROINVERTEBRATES
Sediment chemistry data and toxicity data provide indications of sediment quality, but only
indirect estimates of ecological impact. A goal of the Harbor management plan is to establish
and maintain a healthy and productive ecosystem. Achieving this requires an understanding of
the effects of contaminants on indigenous communities, as well as the extent and magnitude of
those effects.
Bottom-dwelling invertebrates (benthos) have several characteristics that make them useful
indicators of biological response to environmental conditions. Because they live and feed in the
sediments, they are directly exposed to contaminant effects. Benthos are relatively sedentary
and cannot avoid exposure, therefore they can provide an accurate indication of local
environmental conditions. Bottom dwelling organisms are also relatively long-lived and are an
important link between primary producers and higher trophic levels. Additionally, benthos
exhibit a broad diversity of sizes, feeding modes and life history characteristics, with a range of
responses to environmental stress, making them especially suitable as integrators of contaminant
effects.
There are many individual measures that have been developed for describing benthic
communities. This study used several structural measures to quantify the status of benthic
macroinvertebrate assemblages (Table 2-4). Species diversity is indicative of site biodiversity.
Biodiversity is measured here as the number of species present (i.e., species richness) and
species diversity (Shannon-Wiener index). Evenness (distribution among species in the
community) is incorporated in the Shannon-Weiner index (Shannon and Weaver, 1949).
Biomass is an integral component of community structure, since it is the basis for energy flow
and has been shown to be responsive to pollution stress (Warwick, 1986; Luckenbach et al.,
1990). Total abundance is used as an indicator for contaminant effects (Becker et al., 1990)
and, along with biomass, is a measure of total biological activity at a site. The use of benthic
species that are pollution-tolerant or pollution-sensitive has been used to determine the
ecological health of a location (Grassle and Grassle, 1974 and 1976). In the previous
investigation (Adams et al.,1998), lists of pollution-sensitive and pollution-indicative species
were developed for the Harbor (Appendix C).
However, more than one measure or indicator, combined into an index of benthic invertebrate
structure, can distinguish more effectively than individual measures between normal and
abnormal benthic assemblages. A multi-metric benthic index of biotic integrity (B-IBI), similar
to the fresh water Index of Biotic Integrity (IBI) (Karr, 1991; Kerans and Karr, 1994) was
developed for the NY/NJ Harbor (Adams et al., 1998). Five metrics which most effectively
distinguished normal sites from all others were selected for the B-IBI; these metrics were
6-1
-------
evaluated for four different salinity and grain size habitats. The index was calculated by scoring
each selected metric as 5, 3, or 1 depending on whether its value at a site approximated, deviated
slightly from, or deviated greatly from conditions at the best reference sites. The B-IBI value for
each station is calculated as the mean score of the five metrics. A mean score of 5 indicated that
the site was approximately equivalent to the best reference sites. A score of 3 or 1 indicated that
the site slightly deviated or greatly deviated from conditions at the best reference sites and would
be considered to have impacted benthos.
Diversity and Taxonomic Composition
A total of 278 infaunal species were represented in the Harbor in 1998 (Table 6-1). The mean
number of species per sample in the entire Harbor was 19.2 (Table 6-2). Mean species diversity
(Shannon-Wiener) in the Harbor was 2.6 (Table 6-2). Pollution sensitive species accounted for
9.2 % of the Harbor benthic organisms, while pollution-indicative species comprised 19.7 % of
the benthos (Table 6-2).
Table 6-1 Species Richness (Total Number of Species)
Number of Species
Harbor
1993/4
239
1998
278
Jamaica
Bay
1993/4
137
1998
161
Newark
Bay
1993/4
91
1998
125
Lower
Harbor
1993/4
166
1998
218
Upper
Harbor
1993/4
152
1998
144
Newark Bay has the least number of species of all the sub-basins and Lower Harbor the most
(Table 6-1). Shannon-Wiener diversity was similar in all sub-basins, but taxonomic composition
varied greatly among sub-basins.
Table 6-2. Means of Benthic Variables (± 90% confidence interval)
Species Richness
(as # species/
sample)
Pollution- S ensitive
Species (%)
Pollution-Indicative
Species (%)
Species Diversity
(Shannon- Wiener)*
Harbor
1993/4
19.2
±1.7
13
±5.6
31
±3.5
2.3
±0.17
1998
24.5
±2.0
9.2
±2.4
19.7
±2.2
2.6
±0.58
Jamaica
Bay
1993/4
17.7
±2.7
3.6
±2.0
46
±8.4
2.1
±0.20
1998
20.6
±4.0
6.4
±2.1
27.3
±3.8
2.1
±0.17
Newark
Bay
1993/4
14.1
±2.6
0.3
±0.3
65
±7.1
2.1
±0.3
1998
17.1
±3.1
1.1
±1.0
46.6
±6.4
2.5
±0.16
Lower
Harbor
1993/4
20.6
±2.6
18
±8.6
20
±5.0
2.4
±0.26
1998
27.4
±3.4
11.2
±4.8
11.4
±3.5
2.7
±0.22
Upper
Harbor
1993/4
17.1
±2.3
6.8
±5.6
49
±6.3
2.5
±0.15
1998
19.8
±3.4
6.8
±4.6
33.4
±8.6
2.5
±0.21
* natural log calculation
6-2
-------
Between 1993/4 and 1998, the total number of species and the mean number of species per
sample in the Harbor, as well as in each of the sub-basins, slightly increased. Species diversity
in the Harbor and its sub-basins remained the same or slightly increased. The percentage of
pollution-indicative species showed statistically significant decreases across the Harbor sub-
basins, while pollution-sensitive species remained similar between sampling periods. Dependent
on the sub-basin, there were no statistically significant changes in pollution-sensitive species
between 1993/4 and 1998. In 1998,
D Other Species I Amphipoda G Mollusca I Polychaeta
300
Figure 6-1. Numbers of benthic macrofaunal species, by major taxon.
identified (Figure 6-1).
pollution-sensitive species were
significantly less abundant in Newark
Bay than elsewhere in the Harbor, and
more abundant in Lower Harbor.
In the Harbor and in each sub-basin,
one-third to one-half of the total
number of species were consistently
polychaetes (Figure 6-1). Molluscs
and arthropods were represented by
approximately equal numbers of
species in each sub-basin. Among the
sub-basins, amphipod species
comprised 17 to 21% of all species
identified. Three taxa (Amphipoda,
Mollusca, and Polychaeta) include
about 77% of all Harbor taxa
Abundance and Biomass
The mean abundance and biomass for the Harbor in 1998 were 18,000 organisms/m2 and 10.2
g/m2, respectively (Table 6-3). These numbers are both significantly less than those recorded in
1993/4.
The mean abundance was significantly lower in both Newark Bay and Upper Harbor than in any
other Harbor sub-basin in 1998 (Table 6-3). Biomass of the benthos was lowest in Newark Bay.
Comparison of 1998 to 1993/4 shows mean abundance and biomass have significantly decreased
in the Harbor and in individual sub-basins. Jamaica Bay showed the least change in abundance
with a slight increase in biomass. Lower Harbor had a large decrease in organism abundance,
while both the Lower Harbor and Upper Harbor saw a significant decrease in biomass.
-------
Table 6-3. Abundance and Biomass Means (± 90% confidence interval)
Abundance (#
organisms/m2)
Biomass (g/m2)
Harbor
1993/4
40,000
±14,000
31
±11
1998
18,000
±98
10
±4
Jamaica
Bay
1993/4
39,000
±15,000
10
±5
1998
34,000
±17,000
13
±5
Newark
Bay
1993/4
11,000
±4,700
5
±2
1998
5,900
±2,000
5
±7
Lower
Harbor
1993/4
52,000
±22,000
50
±31
1998
20,000
±8,000
11
±12
Upper
Harbor
1993/4
12,000
±3,600
56
±35
1998
8,000
±2,000
9
±7
Benthic Index
Approximately 31 % of the Harbor area exhibited measurable departure from the structure at
reference sites (Table 6-4). Most of this area (20%) was in a moderately impacted category (B-
IBIvaluesof2to<3).
Measurable benthic impacts (B-IBI<3) were most widespread in Newark Bay, Upper Harbor and
Jamaica Bay (Figure 6-2). Estimates of impacted benthic area ranged from 18% for Lower
Harbor to 89% for Newark Bay (Table 6-4). The distribution of individual stations with
impacted benthos (Figure 6-3) shows the most highly impacted sites were located in the Newark
Bay sub-basin and in the back bay portion of Jamaica Bay. Newark Bay had three stations of 28
that were comparable to reference conditions (Appendix D).
A comparison with 1993/4 data shows that for the Harbor overall the percent of area with the
most impacted benthic communities has remained similar between studies. However, there has
been a shift of significant portions of the Harbor from the moderately impacted category to the
unimpacted category. Within the sub-basins, this shift is also seen, except in Newark Bay.
Table 6-4. Percent of Area within B-IBI categories (+ 90% C.I.)
lto<2
impacted
2to<3
moderately
impacted
>3-5
unimpacted
Harbor
1993/4
6
(3-9)
47
(37-57)
47
(37-58)
1998
11.1
±1.5
20.3
±3.9
68.6
±3.9
Jamaica
Bay
1993/4
18
(9-31)
46
(33-60)
36
(24-50)
1998
14.3
±10.9
32.1
±14.5
53.6
±15.5
Newark
Bay
1993/4
18
(0-38)
80
(60-100)
2
(0-6)
1998
60.7
±15.1
28.6
±14.0
10.7
±9.6
Lower
Harbor
1993/4
0
(0-8)
39
(27-53)
61
(47-73)
1998
0
17.9
±11.9
82.1
±11.9
Upper
Harbor
1993/4
14
(6-27)
61
(47-73)
25
(14-38)
1998
28.0
±14.7
20.0
±13.1
52.0
±16.4
6-4
-------
Benthic Index of Biotic Integrity
d Unimpacted benthos: B-IBI value = 3.00 - 5.00
O Moderately impacted benthos: B-IBI value = 2.00 - 2.90
A Highly impacted benthos: B-IBI value = 0.00 -1.90
o £ Upper Harbor
D
D
NEW
JERSEY
Newark Bay
Raritan
Bay
10
Sandy Hook Bay
Figure 6-2. B-IBI scores of individual stations.
6-5
-------
SUMMARY and
RECOMMENDATIONS
Summary
The CCMP for the NY/NJ Harbor (1996) set out goals for the protection and restoration of the
NY/NJ Harbor system. Key to achieving these goals are understanding of the current chemical
and ecological condition of the system and how the system responds over time to the
management actions that have been implemented and the natural changes that have occurred.
A previous investigation (Adams et al., 1998) developed a baseline of chemical, biological, and
toxicity estimates for the Harbor and each of its sub-basins. The current investigation took place
five years after the baseline and measured the same parameters to determine how conditions
were changing in the Harbor. During each investigation, twenty-eight probabilistically selected
stations were sampled in four sub-basins of the Harbor: Jamaica Bay, Newark Bay, Upper
Harbor, and Lower Harbor.
While some aspects of sediment quality in the Harbor have remained the same, some have shown
improvement.
> The Harbor is still extensively contaminated with chemical substances at levels of
concern but there has been improvement:
> Harbor means for mercury and DDT exceeded ERMs (similar to 1993/4)
> Harbor means for all chemicals exceeded or equaled their ERLs, except
antimony and cadmium (similar to 1993/4 except for antimony which did
not exceed its ERL then)
> Total chlordane means have had a statistically significant decrease in all
sub-basins, except the Upper Harbor
> Dioxin and furan concentrations have not significantly changed
> Forty-five percent of the Harbor exceeded an ERM for at least one
contaminant (compared to 50% in 1993/4)
7-1
-------
> Mercury is the most ubiquitous contaminant at a level of concern
» 68% of the Harbor exceeded the ERL, 42% exceeded the ERM
(75% and 34% in 1993/4)
* Areal PAH contamination has not significantly changed between 1993/4
and 1998
Benthic (bottom dwelling) organisms and associated measures have shown mixed
results
> Sixty-nine percent of the Harbor had un-impacted benthic communities
(compared to 47% in 1993/4)
> Newark Bay had the most area with impacted benthos (89%) in
1998, compared to 98% in 1993/4)
> Most sub-basins (except Newark Bay) have had a shift of area
from the moderately impacted category to the unimpacted column
> Pollution-indicative species were generally distributed inversely to
pollution-sensitive species
> Pollution-indicative species were least abundant in Lower Harbor
and most abundant in Newark Bay
> Benthic abundance and biomass have decreased or stayed the same
Harbor-wide and in the sub-basins from 1993/4 to 1998
The extent and distribution of sediment toxicity in the Harbor has remained stable
> Twelve percent of the Harbor was toxic to Ampelisca abdita (15% in
1993/4)
> Newark Bay has the most toxic area (50%), compared to 46% in 1993/4
7-2
-------
Recommendations
Evaluate the sampling interval (currently 5 years)
It is very likely that major changes in the Harbor had already occurred before the 1993/4
and 1998 investigations. Five years may not be long enough to distinguish additional
change.
Add an additional measure of sediment toxicity.
The Ampelisca abdita assay has been criticized as lacking sensitivity. Sediment
porewater toxicity tests have been shown to be more sensitive than Ampelisca (Carr and
Chapman, 1992; Carr et al., 2000) and have excellent correspondence with bulk sediment
contaminant concentrations (Carr et al., 1996).
Evaluate the addition of analytes that are not currently measured but may be responsible
for biological effects.
PCB15 has been linked with toxicity in the Harbor but is not measured with the present
listofPCBs.
Nonylphenol is a persistent organic with endocrine disrupting potential that has been
found in sediments of the Harbor in high concentrations.
Organomercury compounds are highly toxic, bioaccumulative and have been found in the
Harbor.
Planar PCBs exhibit toxicity similar to dioxins and also have been found in the Harbor.
Intensify sampling for some parameters.
In situ dissolved oxygen monitoring could provide temporally comprehensive
measurement of condition.
-------
REFERENCES
Adams, D.A. 1998. QUALITY ASSURANCE PROJECT PLAN (QAPP): Trend Assessment
in the NY/NJ Harbor: Including Application of Biological Markers of Exposure and Effect.
USEPA-Region 2, Division of Environmental Science and Assessment, Edison, NJ.
Adams, D.A., J.S. O'Connor, and S.B. Weisberg. 1998. Final Report: Sediment Quality of
the NY/NJ Harbor System- An Investigation under the Regional Environmental Monitoring and
Assessment Program (REMAP). EPA/902-R-98-001. USEPA-Region 2, Division of
Environmental Science and Assessment. Edison, NJ.
www.epa.gov/emap/remap/html/docs/nynjharbor.html
ASTM. 1993. Standard guide for conducting 10-day static sediment toxicity tests with marine
and estuarine amphipods, E1367-92. American Society for Testing Materials, Philadelphia, PA.
Becker, D.S., G.R. Bilyard, and T.C. Ginn. 1990. Comparisons between sediment bioassays
and alterations of benthic macroinvertebrate assemblages at a marine Superfund site:
Commencement Bay, Washington. Environ. Toxicol. & Chem. 9:669-685.
Carr, R.S. and D.C. Chapman. 1992. Comparison of whole sediment and pore-water toxicity
tests for assessing the quality of estuarine sediments. Chem. Ecol. 7:19-30.
Carr, R.S., D.C. Chapman, C.L. Howard and J.M. Biedenbach. 1996 Sediment quality
triad assessment survey in the Galveston Bay Texas system. Ecotoxicology 5:341-364.
Carr, R.S., P.A. Montagna, J.M. Biedenbach, R. Kalke, M.C. Dennicutt, R. Hooten, and G.
Cripe. 2000. Impact of stormwater outfalls on sediment quality in Corpus Christi Bay, Texas,
USA. Environmental Toxiciology and Chemistry, 28:69-77.
Chambers, L., P. Gardinali, J.L. Sericano, and T.L. Wade. 1998. Quantitative
Determination of Tetra- Through Octa-Polychlorinated Dibenzo-p-dioxins and Dibenzofurans by
Isotope Dilution High Resolution Gas Chromatography/High Resolution Mass Spectrometry. In:
NOAA Technical Memorandum NOS ORCA 130, Sampling and Analytical Methods of the
National Status and Trends Program Mussel Watch Project: 1993-1996 Update.
3-1
-------
Cura, J.J., W.J. Heiger-Bernays and K.W. Bucholz. 1995. Draft Program Guidance Manual.
Guidance on Managing Dredged Material Contaminated with Dioxins and Furans, (EPA
Contract No. 68-C2-0134. Work Assignment 2-127). Menzie-Cura and Associates, Inc.,
Chelmsford, MA and Battelle Ocean Sciences, Duxbury, MA.
DiToro, D.M., J.D. Mahoney, D.J. Hansen, K.J. Scott, M.B. Hicks, S.M. Mayr, and M.S.
Redmond. 1990 . Toxicity of cadmium in sediments: the role of acid volatile sulfide. Environ.
Toxicol. Chem. 9:1487-1502.
Frithsen, J.B., Scott, L., and J.A. Ranasinghe. 1994 Analysis of REMAP 1993 New
York/New Jersey Harbor System Benthic Samples. Versar, Inc., Columbia, MD.
Grassle, J.P., and J.F. Grassle. 1974. Opportunistic life histories and genetic systems in
marine benthic polychaetes. J. Mar. Res. 32:253-284.
Grassle, J.P., and J.F. Grassle. 1976. Sibling species in the marine pollution indicator
Capitella (Polychaeta). Science 192:567-569.
Hollander, M., and D.A. Wolfe. 1973. Nonparametric Statistical Methods. John Wiley and
Sons, New York, New York.
Holt, D. and T.M.F. Smith. 1979. Post stratification. J.R. Statist. Soc. A. 142:33-46.
Karr, J.R. 1991. Biological integrity: along-neglected aspect of water resource management.
Ecol.Appl. 1:66-84.
Kerans, B.L. and J. R. Karr. 1994. A benthic index of biotic integrity (B-IBI) for rivers of
the Tennessee Valley. Ecol.Appl. 4:768-785.
Lauenstein, G.G. and A.Y. Cantillo (eds). 1993a NOAANOS ORCA Tech Memo 71:
Sampling and Analytical Methods of the NS&T Program National Benthic Surveillance and
Mussel Watch Projects. Volume: IV. Comprehensive Descriptions of Trace Organic Analytical
Methods. Silver Spring, MD.
Lauenstein, G.G. and A.Y. Cantillo (eds). 1993b. NOAANOS ORCA Tech. Memo. 71:
Sampling and Analytical Methods of the NS&T Program National Benthic Surveillance and
Mussel Watch Projects. Volume: III. Comprehensive Descriptions of Elemental Analytical
Methods. Silver Spring, MD.
Long, E.R. and L.G. Morgan. 1991. The potential for biological effects of sediment-sorbed
contaminants tested in the National Status and Trends Program. NOAA Technical
Memorandum, NOS OMA 52. U.S. National Oceanic and Atmospheric Administration, Seattle,
Washington.
8-2
-------
Long, E.R., D.D. MacDonald, S.L. Smith, and F.D. Calder. 1995 Incidence of adverse
biological effects within ranges of chemical concentrations in marine and estuarine sediments.
Env. Manage. 19:81-97.
Luckenbach, M. W., R.J. Diaz, E.C. Zobrist, and C.H. Button. 1990 Evaluation of the
benthic resource value of impounded and non-impounded tidal creeks in Virginia, USA. Ocean.
Shore Manage. 14:35-50.
NOAA (National Oceanic and Atmospheric Administration). 1995. The Utility of AVS/EqP
in Hazardous Waste Site Evaluations. NOAA Technical Memorandum NOS ORCA 87. Seattle,
Washington.
NYSDEC (New York State Department of Environmental Protection). 1999 Technical
guidance for screening contaminated sediments. NYSDEC, Division of Fish, Wildlife and
Marine Resources, Albany, NY.
NYCDEP (New York City Department of Environmental Protection). 1999 1998 New
York Harbor Water Quality Survey. NYCDEP, Bureau of Wastewater Pollution Control. Wards
Island, NY. www.ci.nyc.ny.us/dep
Reifsteck, D.M., C.J. Strobel and D. Keith. 1993. Environmental Monitoring and Assessment
Program, Near Coastal Component, 1993 Virginian Province Effort, Field Operations and Safety
Manual. U.S. Environmental Protection Agency, ORD, Narragansett, RI.
SAS Institute Inc. 1989. SAS/STAT User's Guide, Version 6, Fourth Edition, Volume 2. Cary,
NC:SAS Institute Inc.
Shannon, C.E. and W. Weaver. 1949. The Mathematical Theory of Communication.
Urbana: University of Illinois Press.
Strobel, C.J., H.W. Buffum, S.J. Benyi, E.A. Petrocelli, D.R. Reifsteck and D.J. Keith.
1995. Statistical Summary: EMAP-Estuaries Virginian Province - 1990 to 1993. EPA/620/R-
94/026. U.S. Environmental Protection Agency, National Health and Environmental Effects
Research Laboratory-Atlantic Ecology Division, Narragansett, RI.
Swartz, R.C. 1999. Consensus sediment quality guidelines for poly cyclic aromatic
hydrocarbon mixtures. Environ. Toxicol. Chem. 4:780-787.
Thursby, G.B., J. Heltshe and K.J. Scott. 1997. Revised approach to toxicity test
acceptability criteria using a statistical performance assessment. Environ. Toxicol. Chem. 16(6).
-------
U.S. EPA-Region 2. 1996. New York- New Jersey Harbor Estuary Program, Final
Comprehensive Conservation and Management Plan (CCMP). U.S. Environmental Protection
Agency, Water Management Division, New York, New York.
U.S. EPA. 1983. Methods/or Chemical Analysis of Water and Wastes, EPA-600/4-79-020.
U.S. Environmental Protection Agency, Environmental Monitoring and Support Laboratory,
Cincinnati, OH.
U.S. EPA. 1989. Interim Procedures for Estimating Risks Associated with Mixtures of
Chlorinated Dibenzo-p-Dioxins and -Dibenzofurans (CDDs and CDFs) and 1989 Update. U.S.
Environmental Protection Agency, Risk Assessment Forum, Washington, DC. EPA/625/3-
89/016.
U.S. EPA. 1998. Test Methods for Evaluating Solid Waste, Physical/Chemical Methods (SW-
846). U.S. Environmental Protection Agency, Office of Solid Waste, Washington, D.C.
http ://www. epa. gov/epaoswer/hazwaste/test/main.htm
U.S. EPA. 1995. Environmental Monitoring and Assessment Program (EMAP) Laboratory
Methods Manual: Estuaries, Volume 1: Biological and Physical Analyses. U.S. Environmental
Protection Agency, Office of Research and Development, Narragansett, RI. EPA/620/R-95/008.
www.epa.gov/emap/html/pubs/docs/groupdocs/estuary/field/labman.html
U.S. EPA. 2001. Workshop Report on the Application of 2,3,7,8-TCDD Toxicity Equivalence
Factors to Fish and Wildlife. EPA/630/R-01/002. Risk Assessment Forum, NCEA, Washington,
D.C. www.epa.gov/ncea/raf/pdfs/tefworkshopforum.pdf
U.S. EPA and U.S. Army Corps of Engineers (U.S. ACE). 1991. Evaluation of dredged
material proposed for ocean disposal - testing manual, EPA-503/8-91/001. U.S. Environmental
Protection Agency, Office of Water, Washington, DC and U.S. Army Corps of Engineers,
Washington, DC.
Warwick, R.M. 1986. A new method for detecting pollution effects on marine macrobenthos
communities. Mar. Biol. 92:557-562.
8-4
------- |