tPA
United States
Enviror.Tients;
Agency
Oi: and Soecia' Materials
Cornroi Division
Marine Protectior. Branch
Washington DC 2045C
November 1979
Water
Statement (El
for New York
Designation
ight Ac
Site
1. NEW YORK BIGHT ACID
WASTES DISPOSAL SITE
2. NORTHERN AREA *
3. SOUTHERN AREA
A. DELAWARE BAY ACID
WASTES DISPOSAL SITE
5. 106-MILE CHEMICAL
WASTES DISPOSAL SITE
•
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DRAFT
ENVIRONMENTAL IMPACT STATEMENT (EIS)
for
NEW YORK BIGHT ACID WASTE
DISPOSAL SITE DESIGNATION
November 1979
&EPA
Prepared Under Contract 68-01-4610
T. A. Wastler, Project Officer
for
U.S. ENVIRONMENTAL PROTECTION AGENCY
Oil and Special Materials Control Division
Marine Protection Branch
Washington, D.C. 20460
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ENVIRONMENTAL PROTECTION AGENCY
DRAFT
ENVIRONMENTAL IMPACT STATEMENT ON
THE NEW YORK BIGHT ACID WASTE DISPOSAL
SITE DESIGNATION
Prepared by: U.S. Environmental Protection Agency
Oil and Special Materials Control Division
Marine Protection Branch
Washington, D.C. 20460
Approved by:
T. A. Wastler Date
Project Officer
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SUMMARY SHEET
ENVIRONMENTAL IMPACT STATEMENT
FOR
NEW YORK BIGHT ACID WASTE DISPOSAL SITE DESIGNATION
(X) Draft
( ) Final
( ) Supplement to Draft
ENVIRONMENTAL PROTECTION AGENCY
OFFICE OF WATER PROGRAM OPERATIONS
MARINE PROTECTION BRANCH
1. Type of Action
(X) Administrative/Regulatory action
( ) Legislative action
2. Brief background description of action and purpose.
The proposed action is the designation of the New York Bight Acid Waste
Disposal Site for continuing use. The site is approximately 15 nautical
miles east of Long Branch, New Jersey and south of Long Beach, Long
Island, New York. The site is used by two industries in the New Jersey
area. The purpose of the action is to provide an environmentally
acceptable area for the disposal of wastes that will comply with EPA's
rigid marine environmental impact criteria.
3. Summary of major beneficial and adverse environmental and other impacts.
The major benefit of the proposed action is to provide an environmentally
acceptable location for the disposal of.acid wastes for which land-based
treatment methods are not yet satisfactory.
-------
Wastes have been disposed at the Acid Site since 1948 and long-term
adverse effects caused by the various wastes have not been demonstrated.
There are short-term adverse effects, especially upon plankton, but the
ecosystem rapidly recovers. EPA's permit program mitigates such adverse
effects where possible. No environmental effects caused by waste
disposal at the Acid Site are irreversible or irretrievable.
4. Major alternatives considered.
The alternatives considered in this EIS are:
(1) No Action - The site would continue with an interim designation.
This is not a viable alternative since the EPA is required to decide
the fate of this site; i.e., final designation or end of dumping at
the site.
(2) Proposed action - Use the existing Acid Site for the continued
disposal of these wastes.
(3) Alternative sites - Use another ocean site for these wastes: the
106-Mile Chemical Waste Disposal Site and the Northern and Southern
areas near the Hudson Canyon.
5. Comments have been requested from the following:
Federal Agencies and Offices
Council on Environmental Quality
Department of Commerce
Maritime Administration
National Oceanic and Atmospheric Administration (NOAA)
Department of Defense
Army Corps of Engineers (CE)
Department of the Air Force
Department of the Navy
VI
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Department of Health, Education, and Welfare
Department of the Interior
Bureau of Land Management
Bureau of Outdoor Recreation
Fish and Wildlife Service
Geological Survey
Department of Transportation
Coast Guard
National Aeronautics and Space Administration (NASA)
National Science Foundation
Water Resources Council
States and Municipalities
Connecticut, Delaware, Maryland, Massachusetts, New Jersey, New York,
Pennsylvania, Rhode Island, Virginia
Private Organizations
American Chemical Society
American Eagle Foundation
American Littoral Society
Audubon Society
Center for Law and Social Policy
Environmental Defense Fund, Inc.
Freeport (Li) Boatmen's Association
Manufacturing Chemists' Association
National Academy of Sciences
National Wildlife Federation
Resources for the Future
Sierra Club
United Boatmen of New Jersey
Water Pollution Control Federation
VII
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Academic/Research Institutions
Lamont-Doherty Geological Observatory
New York State University
Rutgers University
University of Delaware
University of Rhode Island
Woods Hole Oceanographic Institution
Permittees
Allied Chemical Corp.
ML Industries, Inc.
6. The draft statement was officially filed with the Director, Office of
Environmental Review, EPA, on December 6, 1979.
7. The 60-day review period for comments on the Draft EIS will end on
-February 12, 1979.
Comments should be addressed to:
Mr. T.A. Wastler
Chief, Marine Protection Branch (WH-548)
Environmental Protection Agency
Washington, D.C. 20460
Copies of the Draft EIS may be obtained from:
Environmental Protection Agency
Marine Protection Branch (WH-548)
Washington, D.C. 20460
Environmental Protection Agency
Region II
Marine & Wetland Protection Branch
26 Federal Plaza
New York, NY 10007
Vlll
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The draft statement may be reviewed at the following locations:
Environmental Protection Agency
Public Information Reference Unit, Room 2404 (Rear)
401 M Street, SW
Washington, D.C.
Environmental Protection Agency
Region II
Library, Room 1002
26 Federal Plaza
New York, N.Y.
Environmental Protection Agency
Region II
Woodbridge Ave.
GSA Raritan Depot
Edison, N.J.
NOAA/MESA New York Bight Project
Old Biology Bldg.
State University of New York
Stony Brook, N.Y.
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SUMMARY
This Environmental Impact Statement (EIS) provides the public
information required for the decision-making process about
formal designation of the New York Bight Acid Waste Disposal
Site for continued use as an ocean disposal site. It
recommends the types of wastes that could be released at the
site, summarizes the history of waste disposal at the site,
and provides guidance for the U.S. Environmental Protection
Agency (EPA) to manage the site under the ocean dumping
permit program.
ORGANIZATION OF THE ENVIRONMENTAL IMPACT STATEMENT
The EIS has three levels of detail: This summary highlights significant
points of the chapters, permitting readers to understand major points without
reading the entire text. The main text contains additional technical
information, with full discussions of the options and decisions. The
appendixes contain supplemental technical data and information which amplify
and support the decisions. It is not necessary to read the appendixes to
understand the rest of the document.
Four chapters comprise the main body of the EIS:
• Chapter 1 specifies the purpose and necessity of the proposed
action and presents background relevant to ocean waste disposal.
The legal framework EPA uses to select, designate, and manage ocean
waste disposal sites is described.
• Chapter 2 presents alternatives to designating the Acid Site,
describes the procedures by which alternatives were chosen and
evaluated, and summarizes the relevant comparisons of all
alternatives.
• Chapter 3 describes the environmental features of the Acid Site and
the alternatives. The history of waste disposal and other
activities in the site vicinities is fully described.
XI
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• Chapter 4 discusses the environmental consequences of waste disposal
at the alternative sites and at the proposed location.
*
Five appendixes are included to support the text:
• Appendix A specifies the environmental characteristics of the New
York Bight and describes the oceanographic processes occurring at
the Acid Site.
• Appendix B discusses the Acid Site in detail, specific studies that
have been performed at the site, and unique features.
• Appendix C describes the waste inputs to the New York Bight from all
contaminant sources.
• Appendix D discusses the previous waste disposal at the Acid Site
and compares these inputs to the total waste loading.
• Appendix E summarizes the existing monitoring plan at the site and
defines general criteria for future site monitoring.
BACKGROUND
The Council on Environmental Quality (CEQ) identified ocean waste disposal
as a potentially serious environmental problem (CEQ, 1970). As a result of
CEQ's report and increasing public awareness of the dangers of unregulated
waste disposal in the oceans, Congress passed the Marine Protection, Research
and Sanctuaries Act (MPRSA) in 1972. This law placed the ocean disposal of
barged wastes under the authority of EPA, which published the Final Ocean
Dumping Regulations and Criteria in 1977 (which superseded regulations
published in 1973). This was designed to regulate waste disposal, evaluate
environmental effects of various waste types, and designate and manage all
XII
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ocean disposal sites for continued use. These regulations identified 13
interim municipal and industrial waste disposal sites for use until waste
disposal operations were terminated, or until sites were designated for use,
in accordance with all regulations. The subject of this EIS is the
designation of the New York Bight Acid Waste Site for continued use.
PROPOSED ACTION
EPA proposes to designate the New York Bight Acid Waste Disposal Site (Acid
Site) for continued use for liquid acid waste disposal. This action will
fulfill the need for a suitable location in the New York-New Jersey offshore
area for disposal of certain wastes which comply with the criteria for ocean
disposal, under EPA's ocean dumping permit program.
The Acid Site was first used in 1948. Only two industrial waste
generators, NL Industries, Inc., and Allied Chemical Corp., are presently
(1979) using the site for disposal of highly acidic waste. Acids in the waste
are rapidly neutralized by seawater. Other waste constituents, present in
minute quantities, have no apparent impact on the marine environment. NL
Industries and Allied Chemical have each submitted reports to EPA, which
demonstrate that their respective wastes comply with the environmental impact
criteria of the Ocean Dumping Regulations. Land-based alternative disposal
methods are currently less environmentally acceptable and more costly than
ocean disposal; therefore ocean disposal of such wastes is environmentally
preferred until suitable alternatives can be implemented.
Continued use of the existing interim site in the Apex of the New York
Bight is the preferred alternative for several reasons. More than 30 years of
studies have not documented any long-term adverse effects from acid waste
disposal at this site. The amount of pollution introduced by acid waste is
slight when compared with other sources, thus the transference of waste
disposal activities to a more distant site would not environmentally
counterbalance increased economic costs (to the waste generators and the
Federal Government) and logistic difficulties of using a new site.
Xlll
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MAJOR ALTERNATIVES
The major alternatives to designation of the Acid Site are:
(1) No action - The site would continue with an interim designation.
This is not a viable alternative since the EPA is required to decide
the fate of this site; i.e., final designation or end of dumping at
the site.
(2) Use of alternative ocean disposal sites.
Three other locations, the Northern and Southern Areas in the New York
Bight, and the 106-Mile Chemical Waste Disposal Site located off the
Continental Shelf, were considered as possible alternatives to the existing
site. The following listing shows the category of each alternative site.
Site
Category
New York Bight Acid
Waste Disposal Site
Existing site located on the
Continental Shelf
106-Mile Chemical
Waste Disposal Site
Existing site located off the
Continental Shelf
Northern Area
Southern Area
New site located on the
Continental Shelf offshore
Long Island
New site located on the
Continental Shelf offshore
New Jersey
xiv
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Nine municipal and industrial waste disposal sites (excluding dredged material
disposal sites) exist in the mid-Atlantic region. (See Figure 2-2, Chapter
2). Sites used for other types of wastes (cellar dirt, wood incineration,
wrecks, and sewage sludge) were not considered as candidates for acid waste
disposal. Combinations of different waste types at a single site is generally
undesirable because synergistic interactions may occur between the wastes.
The Delaware Bay Acid Waste Site was not considered because of its inactive
status and distance from New York Harbor.
The 106-Mile Site was considered as a viable alternative since it is
presently used for disposal of aqueous industrial wastes, (including acids)
and is located beyond the Continental Shelf. The Northern and Southern Areas
were considered as alternative sewage sludge disposal sites, and site-specific
information is available for both areas. The Alternate Sewage Sludge Site,
(Figure 2-2 in Chapter 2) has been designated in the northeast corner of the
Northern Area. These areas are representative of the mid-shelf region
offshore New Jersey and Long Island. If another specific location were
selected, the same reasoning would apply. Table S-l summarizes the favorable
and unfavorable features of each alternative considered in this EIS.
AFFECTED ENVIRONMENT
The Acid Site is located in the New York Bight Apex. The Apex is adjacent
to one of the most industrialized and populated regions of the country, and
receives wastes from more than 20 million people. Large quantities of acid
wastes are released annually at the site, but adverse effects last only a few
minutes following disposal. When compared with waste inputs from all sources,
the contaminants in acid wastes are insignificant. The existing site is
15 nmi from shore, abuts the Hudson Submarine Canyon, has a sandy bottom, and
is in 26 m of water.
The Northern and Southern Areas are further offshore (30 nmi), with sandy
bottoms in deeper water (31 to 53 m). The Hudson Canyon, an important
geological feature, and a migration route for some animals, lies between the
xv
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TABLE S-l
SUMMARY EVALUATION OF PROPOSED ACTION AND ALTERNATIVES
Alternative
tv.-i Ac t i on
Continue
interim lite
desi gnat i on
Propospd Action
DP si gnatp e.xi st i ng
Si tP
Alternative Sites
Off-the-Continental
Shplf 106-Mile Site
On-the-Continental
Shelf
{ 1 ) Northern Area
( 2 ) bout nprn ArPa
Favorable Factors
None
whi ting, bluefi sh) not harmed
by waste di sposa I .
year*; wi thout apparent p.nv iron-
mental damagp.
moni tori ng e f fects of di sposal
and survei 1 lance of di sposal
programs i s low.
di sposal .
all pprrai tte.es .
aesthetics, or benthos due to
site.
(iiij Site has been used for 14 years
without apparent environ-
mental damage..
(i ) Area does not have large
numbers of commercially
ex pi oi table spec ies .
( i i ) Water movement carries
contaminants off-Shelf and
away from shore.
(iii) Short-term adverse effects on
the water same as at existing
site.
I i ) Short-term adverse effects on
the water same as at existing
si te .
Interi m desi gnat i on
expires January 1 9bU
(i) Altnough d small amount
( 1%) of the total input,
acid wastes are additional
sources of contaminants to
the Ape.x, a highly stressed
area.
visible plume, of ferric
hydroxide (rust ) whi ch is
persistent (48 hours),
aesthetically displeasing
and may intprfere with somp
difficult due to environ-
mental complex! ty.
5-8 times. Primary waste
generator probably could
not use si te and could
shut down plant .
( i i i ) Survei 1 lance and moni tori ng
costs increaspd .
hazard and risk.
(i) Distance from shore
increases hauling costs
3-4 t i mes . Primary waste
generator probably could
not use site and may shut
down plant .
(ii) Survei 1 lance and moni to ring
costs i ncreaspd.
( i i i ) Would con t ami nate an area
where wastes have never been
dumpe.u . Possible accumulations
i n the sediment s .
( i ) Area has potentially
exploitable biotic and
(i i ) Would contaminate an area
where wastes have never been
dumped. Possible, accumu-
lations in the sed iment s .
( i i i ) Economi cal ly , samr aaversp
effects as in Nortnern Are&.
XVI
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two named areas. Potentially exploitable shellfish resources and mineral
resources exist near the Southern Area. The Northern Area is neither unique
nor especially productive.
The 106-Mile Site is located just beyond the edge of the Continental Shelf,
90 nmi from shore, in over 1,500 m of water. The site is oceanic with the
water characteristics and biological features resembling more the open ocean
to the east than coastal areas to the west. Chemical wastes were released
there, beginning in 1961; munitions and low-level radioactive wastes have also
been dumped in this area. Long-term adverse effects caused by such wastes
have not been demonstrated. There are no known exploitable mineral or
biological resources in the area.
ENVIRONMENTAL CONSEQUENCES
Since acid-waste liquids do not have an appreciable solid phase, the short-
term effects after release will be similar at all alternative sites. Three
characteristics of these liquid acid wastes are important in considering
possible effects at the alternative sites:
(1) Aqueous wastes will not measurably affect benthos at deep sites, but
some waste constituents may accumulate in sediment at shallow sites.
(2) Aqueous wastes have short-term (minutes to hours) effects on the
water when released at rates that allow adequate dispersion, thus
preventing accumulation of waste constituents in the water mass.
(3) Bioaccumulation of waste constituents in organisms that inhabit the
water column (plankton or fish) is unlikely.
Acid waste disposal has had minimal adverse impacts on the environment of
the Acid Site in New York Bight. Assessments of over 30 years of docu-
mentation from investigations by Federal, university, and private groups, show
that there are no long-term adverse effects from the wastes. Accumulations of
waste constituents in sediments are possible, but acid wastes represent less
than 1% of total contaminant inputs to the Bight. Consequently, transferring
xv 11
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waste disposals to other locations probably would not measurably improve
either bottom water quality or ecosystem health in the Bight.
The effects of acid waste disposal in the Southern Area could be more
severe than at the existing site. Since wastes have never been released in
the area, detectable accumulations may occur and adversely affect the
ecosystem. It should be noted that potentially exploitable biological
(shellfish) and mineral (oil and gas) resources exist in the area, and waste
disposal operations could interfere with such profitable ocean usage.
If wastes were released in the Northern Area, effects on the ecosystem
would parallel those in the Southern Area. Such effects are potentially more
severe than those resulting from continued use of the existing site. The
adverse effects on public health and water quality would be negligible since
exploitable resources are not found near the site.
If the 106-Mile Site were designated for the disposal of acid wastes, the
effects would be similar to those at the existing nearshore site. Should
adverse environmental effects occur, however, they would be more difficult to
detect because of the inherent complex oceanographic characteristics at the
site. The risk of emergency (short) dumping is further increased because of
the much longer transit time to the site from New York Harbor.
CONCLUSIONS
After carefully evaluating all reasonable alternatives, EPA proposes the
New York Bight Acid Waste Disposal Site for final designation for continued
industrial waste disposal in compliance with the EPA Ocean Dumping Regulations
and Criteria. However, under the Marine Protection, Research, and Sanctuaries
Act of 1972, exploration for alternative ocean disposal areas should continue.
Relevant research and development will be a condition imposed by EPA on waste
generators seeking ocean disposal permits.
XVlll
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Wastes permitted for disposal at the site should have the following
characteristics:
• Aqueous acidic wastes with low concentrations of solids
• Neutrally to negatively buoyant in seawater
• Contain no materials prohibited by the MPRSA
• Demonstrate low toxicity of neutralized wastes to representative
planktonic and nektonic marine organisms
• Contain no constituents in concentrations detectable outside the
site or above-normal ambient levels more than 4 hours after
discharge.
The disposal operations should have the following characteristics:
• Wastes should be discharged from a vessel underway to facilitate
rapid and immediate dilution.
• Each barge load should be sufficiently small to permit adequate
dispersal of the waste constituents before disposal of the next
load so that accumulation of waste materials does not occur due to
successive dumps.
• Except in emergency situations, only one barge should be permitted
within the site for disposal operations within the 4-hour period for
initial mixing.
xix
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CONTENTS
Section Page
1 PURPOSE OF AND NEED FOR ACTION 1-1
FEDERAL LEGISLATION AND CONTROL PROGRAMS 1-3
Marine Protection, Research, and Sanctuaries Act (MPRSA) . 1-5
Ocean Disposal Site Designation 1-8
Ocean Dumping Permit Program 1-12
INTERNATIONAL CONSIDERATIONS 1-14
2 ALTERNATIVES INCLUDING THE PROPOSED ACTION 2-1
NO ACTION ALTERNATIVE 2-3
CONTINUED USE OF THE PROPOSED SITE 2-3
Public Health and Water Quality 2-4
Ecosystem 2-5
Economics 2-7
USE OF ALTERNATIVE EXISTING SITES 2-6
Introduction 2-8
106-Mile Chemical Waste Disposal Site 2-11
USE OF NEW SITES 2-16
Locations on the Continental Shelf 2-17
Location Off the Continental Shelf 2-22
Summary 2-23
DETAILED BASIS FOR SELECTION OF THE PROPOSED SITE 2-24
Geographical Position, Depth of Water,
Bottom Topography and Distance from Coast 2-27
Location in Relation to Breeding, Spawning, Nursery,
Feeding, or Passage Areas of Living Resources in
Adult or Juvenile Phases 2-27
Location in Relation to Beaches and Other Amenity Areas . 2-27
Types and Quantities of Wastes Proposed to be
Disposed of, and Proposed Methods of Release,
Including Methods of Packing the Waste, if Any 2-28
Feasibility of Surveillance and Monitoring 2-28
Dispersal, Horizontal Transport and Vertical Mixing
Characteristics of the Area, Including Prevailing
Current Direction and Velocity 2-28
Existence and Effects of Current and Previous
Discharges and Dumping in the Area (including
Cumulative Effects) 2-29
Interference With Shipping, Fishing, Recreation,
Mineral Extraction, Desalination, Fish and Shellfish
Culture, Areas of Special Scientific Importance
and Other Legitimate Uses of the Ocean 2-29
The Existing Water Quality and Ecology of the Site
as Determined by Available Data, by Trend
Assessment, or Baseline Surveys 2-30
Potential for the Development or Recruitment of
Nuisance Species in the Disposal Site 2-31
xxi
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CONTENTS (Continued)
Page
Section
Existence at, or in Close Proximity to, the Site
of any Significant Natural or Cultural Features
of Historical Importance 2-1
CONCLUSIONS AND PROPOSED ACTIONS ^31
Types of Wastes ~
Waste Loadings ~
Disposal Methods *";"
Disposal Schedules j--\i
Special Conditions
3 AFFECTED ENVIRONMENT
3-1
PROPOSED SITE - NEW YORK BIGHT ACID WASTE SITE 3-1
Site Environment 3-1
Waste Disposal at the New York Bight Acid
Waste Disposal Site 3-8
Other Activities in the Site Vicinity 3-13
Ocean Waste Disposal 3-21
Marine Recreation 3-25
ALTERNATIVE SITE OFF THE SHELF - 106-MILE CHEMICAL WASTE SITE . 3-25
Site Environment 3-25
Waste Disposal at the Site 3-32
Concurrent and Fu ure Studies 3-39
Other Activities in the Site Vicinity 3-39
ALTERNATIVE SITES ON THE CONTINENTAL SHELF 3-40
4 ENVIRONMENTAL CONSEQUENCES 4-1
EFFECTS ON PUBLIC HEALTH AND SAFETY 4-2
Commercial and Recreational Fish and Shellfish 4-3
Navigational Hazards 4-6
EFFECTS ON THE ECOSYSTEM 4-8
Biota 4-9
Water and Sediment Quality 4-15
Emergency Dumping 4-20
UNAVOIDABLE ADVERSE ENVIRONMENTAL EFFECTS AND
MITIGATING MEASURES 4-22
RELATIONSHIP BETWEEN SHORT-TERM USE OF THE SITE AND
LONG-TERM PRODUCTIVITY 4-23
IRREVERSIBLE OR IRRETRIEVABLE COMMITMENTS OF RESOURCES .... 4-24
5 LIST OF PREPARERS 5-1
6 GLOSSARY AND REFERENCES 6-1
xxi i
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CONTENTS (Continued)
APPENDIXES
A ENVIRONMENTAL CHARACTERISTICS OF THE NEW YORK BIGHT A-l
B ENVIRONMENTAL CHARACTERISTICS OF THE NEW YORK BIGHT
ACID WASTE SITE B-l
C CONTAMINANT INPUTS TO THE NEW YORK BIGHT C~l
D CONTAMINANT INPUTS TO THE ACID DISPOSAL SITE D-l
E RECOMMENDED MONITORING E-l
ILLUSTRATIONS
Figure
2-1 The Proposed Site and the Alternative Sites 2-2
2-2 Disposal Sites in the Mid-Atlantic Area 2-10
3-1 Location of New York Bight Acid Waste Disposal Site 3-2
3-2 Distribution of Surf Clams, Ocean Quahogs, and Sea Scallops
in the New York Bight (NOAA-NMFS, 1974c) 3-7
3-3 Benthic Faunal Types in the mid-Atlantic Bight 3-9
3-4 Inputs of Metals to the New York Bight 3-11
3-5 Total Landings of Commercial Marine Food Finfishes in the
New York Bight Area, 1880-1975 3-16
3-6 Total Commercial Landings of Marine Food Shellfishes in the
New York Bight Area, 1880-1975 3-16
3-7 Location of Foreign Fishing off the East Coast of the U.S 3-17
3-8 Gravel Distribution in the New York Bight 3-19
3-9 Oil and Gas Leases in the mid-Atlantic Bight 3-20
3-10 Traffic Lanes in the mid-Atlantic Area 3-22
3-11 Ocean Disposal Sites in the New York Bight 3-23
3-12 Location of the 106-Mile Site 3-27
3-13 Monthly Averages of Oxygen Concentration Versus Depth
at the 106-Mile Site 3-30
XXlll
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CONTENTS (Continued)
TABLES
1-1 Responsibilities of Federal Departments and Agencies for
Regulating Ocean Waste Disposal Under MPRSA 1-7
2-1 Fish Landings by States - 1974 • 2-9
2-2 Summary Evaluation of Alternative Disposal Sites for Acid Waste . . 2-25
3-1 Total Landings in 1974 of Five Major Commercial Finfishes
in the New York Bight 3-15
3-2 Total Commercial Landings in 1974 and 1976 of Important
Shellfish Species in the New York Bight (New York-New Jersey) . . . 3-16
3-3 Beach Attendance at State and National Parks in the
New York-New Jersey Metropolitan Area 1976 3-26
3-4 Waste Volumes, 1973 - 1978 at 106-Mile Chemical Waste Site
in Thousands of Tonnes 3-33
3-5 Projected Volumes, 1979 - 1980, at 106-Mile Chemical Waste Site
(Thousands of Tonnes) 3-34
3-6 Physical Characteristics for the Wastes at the 106-Mile
Chemical Waste Site 3-35
3-7 Average Metal Concentrations (ug/1) for the Wastes at the
106-Mile Chemical Waste Site 3-36
3-8 Toxicity Bioassays for Wastes at the 106-Mile Chemical Waste Site . 3-37
4-1 Distances and Transit Times (Round Trip) to Alternate Sites .... 4-7
4-2 Worst-Case Contribution of Waste Metal Input to the
Total Metal Loading at the New York Bight Acid Wastes Site .... 4-17
4-3 Estimated Waste Metal Input to the Total Metal Loading
at the 106-Mile Site 4-18
4-4 Estimated Waste Metal Input to Total Metal Loading
at the Southern Area 4-20
4-5 Estimated Waste Metal Input to Total Metal Loading
at the Northern Area 4-21
5-1 List of Preparers 5-1
xxiv
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Chapter 1
PURPOSE OF AND NEED FOR ACTION
An ocean disposal site is needed since land-based disposal
methods for some acid wastes cannot be implemented using
existing technology. To fulfill this need, EPA proposes to
designate the New York Bight Acid Waste Disposal Site in
accordance with the January 11, 1977 EPA Ocean Dumping
Regulations and Criteria. This chapter defines the action to
be taken, discusses the history of the regulation of ocean
disposal, and summarizes the legal regime for identifying and
establishing viable options.
Ocean disposal of waste materials has been practiced for generations on an
international scale. In the early 1970's, U.S. legislation and international
agreements were enacted to control the disposal of waste in the marine
environments. This legislation greatly decreased the number of industries and
municipalities using ocean waste disposal and forced the development of
land-based alternatives. However, some industries and municipal waste
treatment facilities produce wastes which cannot (using present-day
technology) be treated or dispersed safely or economically on land, but can be
ocean-dumped without seriously degrading the marir.e environment. Most of this
waste-generating activity is centered around the heavily populated and
industrialized East Coast. To safely meet the needs of ocean waste disposal,
the U.S. Environmental Protection Agency (EPA) proposes to designate the New
York Bight Acid Waste Disposal Site (hereafter referred to as Acid Site) for
continued use.
The Acid Site has been used for waste disposal since 1948. In 1973 EPA
designated this site for use on an interim basis, for disposal of acid wastes.
Only three companies have used the site for waste disposal: (1) NL Industries
Inc., Sayreville, New Jersey; (2) Allied Chemical Corporation Elizabeth, New
Jersey; and (3) the E.I. du Pont de Nemours and Company, Grasselli Plant,
Linden, New Jersey. Since December 1975, only NL Industries and Allied
Chemical have used the site. The projected use of the site (1.4 million
tonnes annually until April 1981) is well below the long-term average
1-1
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(2.3 million tonnes annually from 1958 to 1978). Almost all of the wastes
released at the site have been highly acidic (pH below 1.0); some caustic
wastes (PH about 13) were released by Du Pont-Grasselli before 1976, when
their waste disposal operations were moved by EPA to the 106-Mile Chemical
Waste Site.
Studies of the effects of waste disposal at the Acid Site have been
conducted since 1948. Until 1972 most of the work was conducted by university
scientists and sponsored by NL Industries, Inc., the main user of the site.
In 1973, the NOAA-MESA New York Bight Project assessed the environmental
health of the New York Bight and man's influence on the area. This work, and
all other work performed at the site or in the general area, has not uncovered
significant adverse effects caused by acid waste disposal.
By January 1, 1982 ocean disposal of industrial wastes will be permitted
only for wastes which comply with EPA's environmental impact criteria and
cannot be treated on land for environmental or economic reasons. NL
Industries and Allied Chemical have demonstrated that their wastes comply with
EPA's environmental impact criteria and that technically feasible alternative
disposal methods are environmentally less preferable than continued use of the
site; therefore, a present and future need exists for the continued use of
this site. The reason for this continuing need is threefold: (1) NL
Industries and Allied Chemical each produce wastes that cannot be disposed of
using land-based methods, but can be released safely at the Acid Site without
unreasonable degradation of the marine environment, (2) ocean waste disposal
may be required for other wastes that do not comply with environmental
regulations for land disposal but can be released into the marine environment
without causing irreversible adverse effects, and (3) a site of known
environmental characteristics is required for disposal of some wastes under
emergency conditions.
* One metric ton equals 2,205 Ib. Throughout this EIS, the word tonne will be
used to designate a metric ton and to distinguish it from an English ton.
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As part of the decisionmaking process in designating the Acid Site for
continued use, EPA has investigated all. reasonable alternatives. Two broad
categories of alternatives exist: (1) take no action, which would leave the
existing site with an interim designation, or (2) designate another ocean
location for waste disposal.
After a careful review of the alternatives, EPA has determined that
designation of the New York Bight Acid Waste Site for continued use is the
most favorable course of action. Continued use of the site will permit
approved dumping of the wastes at the site under current ocean dumping
permits, and will provide for the disposal of new wastes which the EPA deems
acceptable for ocean disposal. EPA Region II will manage the site, regulate
times, rates, methods of disposal, and quantities and types of materials
disposed, develop and maintain effective monitoring programs for the site,
conduct disposal site evaluation studies, and recommend modifications in site
use or further designation as necessary.
FEDERAL LEGISLATION AND CONTROL PROGRAMS
Until the early 1970's, there was little regulation of ocean waste
disposal. Limited regulation was primarily derived from the New York Harbor
Act of 1888, which empowered the Secretary of the Army to prohibit disposal of
wastes, except those flowing from streets and sewers, into harbors at New
York, Hampton Roads, and Baltimore. Additionally, the Refuse Act of 1899
prohibited the disposing of materials into navigable waters when disposal
impeded safe navigation. Under these acts, selection of disposal locations by
the U.S. Army Corps of Engineers (CE) and the issuance of permits for ocean
disposal were based primarily upon transportation and navigation factors
rather than environmental concerns.
Public interest in adverse effects of ocean disposal was aroused in 1969
and 1970 by incidents resulting from disposal of warfare agents in the ocean.
Simultaneous studies by the National Oceanic and Atmospheric Administration
(NOAA) and several universities identified potential adverse effects of sewage
sludge and industrial waste disposal in the New York Bight (e.g., Buelow et
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al., 1968; Gross, 1970; Pearce, 1972). In 1970, the Council on Environmental
Quality (CEQ), identified poorly regulated ocean waste disposal as a potential
environmental danger in its Report to the President.
The CEQ's report, and the increasing public awareness of potentially
undesirable effects of poorly regulated ocean waste disposal, were mainly
responsible for the enactment of the Marine Protection, Research, and
Sanctuaries Act (MPRSA) of 1972, the primary U.S. legislation now regulating
barged ocean waste disposal. In late 1972, when it became apparent that
Congress would promulgate an Act to regulate ocean disposal, EPA began to
develop criteria to provide an effective technical basis for the regulatory
program. During the development of the technical criteria, EPA sought advice
and counsel from its own scientists, marine specialists in universities,
industries, environmental groups, and other Federal and State agencies. The
criteria, first published in May 1973, completed in October 1973, and revised
in January 1977, are used to evaluate needs for ocean waste disposal and
potential impacts upon marine environment.
While legislation began almost 100 years ago to control waste disposal in
rivers, harbors, and coastal waters, barged ocean waste disposal was not
specifically regulated in the United States until the October 1972 passage of
the Marine Protection, Research, and Sanctuaries Act (MPRSA, PL 92-532). This
important legislation is discussed here along with relevant Federal
legislation, Federal control programs initiated under MPRSA, and EPA programs
for ocean disposal site designation and issuance of ocean disposal permits.
The Clean Water Act (CWA) of 1977 (PL 95-217) supplanted and superseded
earlier legislation and established a comprehensive regulatory program for
controlling discharge of pollutants from outfalls into navigable waters of the
United States, including ocean waters. The primary objective of the CWA is to
restore and maintain the chemical, physical, and biological integrity of the
nation's waters. The CWA provides for EPA to promulgate criteria to prevent
degradation of the marine environment (Section 403), and to apply such
criteria in the issuance of permits (Section 402). The CWA and MPRSA are the
primary Federal legislative means for control of ocean waste disposal, either
through use of ocean outfalls or offshore disposal sites.
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MARINE PROTECTION. RESEARCH. AND SANCTUARIES ACT (MPRSA)
The MPRSA regulates the transport and release of waste materials in ocean
waters. The act is divided into three parts: (1) Title I, Ocean Dumping, (2)
Title II, Comprehensive Research on Ocean Dumping, and (3) Title III, Marine
Sanctuaries. This EIS responds specifically to Title I, Section 102(c), which
charges EPA with the responsibility for designating sites and times for waste
disposal.
Title I, the primary regulatory vehicle of the act, establishes the permit
program for disposal of dredged and nondredged materials, mandates
determination of impacts, and provides for enforcement of permit conditions.
Title I of the act defines methods for regulating ocean disposal of waste
originating from any country into ocean waters under the jurisdiction or
control of the United States. A permit is required for the following reasons
and may be obtained by any person of any nationality: (1) Any transport of
wastes for ocean disposal in U.S. waters, (2) for transporting waste material
away from any U.S. port, (3) or in a vessel under the U.S. flag for disposal
anywhere in the world's oceans.
Title I prohibits ocean dumping of certain wastes, among them biological,
radiological, and chemical warfare agents, and all high-level radioactive
wastes. Title I was amended in November 1977 (PL 95-153) to prohibit barge
*
disposal of harmful sewage sludge after December 31, 1981. The provisions of
Title I include a maximum criminal fine of $50,000, a jail sentence of up to
1 year for every unauthorized dump or violation of permit requirement, and a
maximum civil fine of $50,000. Furthermore, any individual may seek an
injunction against an unauthorized dumper with possible recovery of all costs
of litigation.
* Harmful sewage sludge is defined by PL 95-153 as sewage sludge that "may
significantly degrade or endanger human health, welfare and amenities, the
marine environment and ecological systems, or economic potential."
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Title II of MPRSA provides for comprehensive research and monitoring of
ocean dumping effects on the marine environment. Under Title II, tne
NOAA-MESA New York Bight Project and Ocean Dumping Program have conducted
extensive survey and laboratory investigations over the past several years at
ocean waste disposal sites in the North Atlantic Ocean. This work aids EPA in
its management of sites by providing data for site-use decisions.
Several Federal agencies share responsibilities under MPRSA (Table 1-1).
The major responsibility is mandated to EPA to review, grant, and enforce
dumping permits for all wastes except dredged materials, and to designate and
manage all disposal sites. In January 1977, EPA issued Final Revised Ocean
Dumping Regulations and Criteria (hereafter the "Ocean Dumping Regulations",
40 CFR, Parts 220 to 229). These regulations established procedures and
criteria for designating and managing ocean disposal sites (Part 228),
reviewing ocean disposal permit applications (Part 222), assessing impacts of
ocean disposal and alternative disposal methods (Part 227), and enforcing
permits (Part 226). Interim disposal sites were authorized pending final
designation for continuation or termination of use. The Acid Site was one of
13 municipal and industrial sites approved for interim use.
The Corps of Engineers (CE) issues permits for disposal of dredged material
after determining compliance of the material with EPA's environmental impact
criteria (40 CFR 227) and is subject to EPA's concurrence. The CE is
responsible for evaluating disposal applications, recommending disposal sites,
and granting dredge material permits; nevertheless, dredged material disposal
sites are designated and managed by EPA.
Under MPRSA, the Secretary of Transportation has assigned responsibility to
the U.S. Coast Guard (USCG) for surveillance of disposal operations to ensure
compliance with the permit conditions and to discourage unauthorized disposal.
Violations are referred to EPA for enforcement. Surveillance includes spot
checks of disposal vessels for valid permits, interception or escorting of
vessels carrying waste, use of shipriders during disposal operations, aircraft
overflights during waste release, and random inspections of land facilities.
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TABLE 1-1. RESPONSIBILITIES OF FEDERAL DEPARTMENTS AND AGENCIES
FOR REGULATING OCEAN WASTE DISPOSAL UNDER MPRSA
Department/Agency
Responsibility
U.S. Environmental Protection Agency
U.S. Department of the Army
Corps of Engineers
U.S. Department of Transportation
Coast Guard
U.S. Department of Commerce
National Oceanic and Atmospheric
Administration
U.S. Department of Justice
U.S. Department of State
Issuance of waste disposal permits,
other than for dredged material
Establishment of criteria for
regulating waste disposal
Enforcement actions
Site designation and management
Overall ocean disposal program
management
Issuance of dredged material
disposal permits
Recommending disposal site locations
Surveillance
Issue regulations for disposal
vessels
Long-term monitoring and research
Marine Sanctuary designation
Court actions
International agreements
All of these methods are used for surveillance at the Acid Site, and
interception and escort by USCG vessels or aircraft are the most common
methods. In addition, the USCG is testing the feasibility and accuracy of an
automatic Ocean Dumping Surveillance System (ODSS) , which is based on
electronic navigation. This system has been field-tested and evaluated by the
USCG for future use in routine surveillance.
Title II of MPRSA charges NOAA to conduct comprehensive monitoring and
research programs on the effects of ocean dumping on the marine environment,
including potential long-term effects of pollution, over-fishing, and
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man-induced changes in oceanic ecosystems. Responsibility for field
investigations of ocean disposal effects is shared with EPA. Title III of
MPRSA authorizes NOAA to designate coastal marine sanctuaries, after
consultation with other affected Federal agencies, and to regulate all
activities within these sanctuaries.
The Department of Justice initiates relief actions in court, upon EPA's
referral, in response to violations of the terms of MPRSA. When necessary,
injunctions to cease ocean dumping are sought. Civil and criminal fines and
jail sentences may be levied, based on the magnitude of the violation. The
Department of State seeks effective international action and cooperation in
protecting the marine environment by negotiating international agreements
*
furthering the goals of MPRSA.
The MPRSA has been amended several times since 1972. Most of the
amendments concern annual appropriations for administration of MPRSA; however,
two amendments are noteworthy. One amendment in Marcti 1974 (PL 93-254)
brought the Act into full compliance with the Convention. Another amendment
(PL 95-153) passed in November 1977, prohibits disposal ot harmful sewage
sludge in ocean waters after i)ecex.j.._i jl, lybi.
OCEAN DISPOSAL SITE DESIGNATION
Under Section 102(c) of the MPRSA, the EPA Administrator is authorized to
designate sites and times for ocean disposal, provided that the waste contains
no prohibited materials and will not unreasonably degrade or endanger human
health, welfare, amenities, marine environment, ecological systems, or
economic potential. EPA, therefore, established criteria for designating
sites in Part 228 of the Ocean Dumping Regulations.
The most significant international negotiation, with respect to ocean waste
disposal is the Convention on the Prevention of Marine Pollution by Dumping of
Wastes and Other Matter (hereinafter referred to as "the Convention" or "the
Ocean Dumping Convention").
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General site-selection criteria are listed in Section 228.5:
(a) The dumping of material* into the ocean will be permitted
only at sites or in areas selected to minimize the
interference of disposal activities with other activities in
the marine environment, particularly avoiding areas of
existing fisheries or shellfisheries, and regions of heavy
commercial or recreational navigation.
(b) Locations and boundaries of disposal sites will be so chosen
that temporary perturbations in water quality or other
environmental conditions during initial mixing caused by
disposal operations anywhere within the site can be expected
to be reduced to normal ambient seawater levels or to
undetectable contaminant concentrations or effects before
reaching any beach, shoreline, marine sanctuary, or known
geographically limited fishery or shellfishery.
(c) If, at any time during or after disposal site evaluation
studies, it is determined that existing disposal sites
presently approved on an interim basis do not meet the
criteria for site selection set forth in [Section] 228.5 to
228.6, the use of such sites will be terminated as soon as
suitable alternate disposal sites can be designated.
(d) The sizes of ocean disposal sites will be limited in order
to localize for identification and control any immediate
adverse impacts and permit the implementation of effective
monitoring and surveillance programs to prevent adverse
long-term impacts. The size, configuration, and location of
any disposal site will be determined as a part of the
disposal site evaluation or designation study.
(e) EPA will, wherever feasible, designate ocean dumping sites
beyond the edge of the Continental Shelf, and other such
sites that have been historically used.
Factors considered under the specific criteria for site selection treat the
general criteria in additional detail. If a proposed site satisfies the
specific criteria for site selection, it meets the broader, general criteria.
Eleven factors are considered in Section 228.6:
• Geographical position, depth of water, bottom topography and
distance from coast.
• Location in relation to breeding, spawning, nursery, feeding,
or passage areas of living resources in adult or juvenile
phases.
• Location in relation to beaches and other amenity areas.
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Types and quantities of wastes proposed to be disposed of and
proposed methods of release, including methods of packing the
waste, if any.
Feasibility of surveillance and monitoring.
Dispersal, horizontal transport, and vertical mixing character-
istics of the area, including prevailing current direction and
velocity, if any.
Existence and effects of current and previous discharges and
dumping in the area (including cumulative effects).
Interference with shipping, fishing, recreation, mineral
extraction, desalination, fish and shellfish culture, areas of
special scientific importance, and other legitimate uses of the
ocean.
The existing water quality and ecology of the site as
determined by available data or by trend assessment or baseline
surveys.
Potentiality for the development or recruitment of nuisance
species in the disposal site.
Existence at, or in close proximity to the site of any
significant natural or cultural features of historical
importance.
These factors are applied to the Acid Site in Chapter 2.
Once designated, the site must be monitored for adverse impacts of waste
disposal. EPA monitors the following effects (listed in Section 228.lOb) to
determine the extent to which the marine environment has been affected by
material released at the site:
• Movement of materials into estuaries or marine sanctuaries, or
onto oceanfront beaches or shorelines.
• Movement of materials toward productive fishery or shellfishery
areas.
Absence from the disposal site of pollution-sensitive biota
characteristic of the general area.
Progressive nonseasonal changes in water quality or sediment
composition at the disposal site when these changes are
attributable to materials disposed of at the site.
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• Progressive nonseasonal changes in composition or numbers of
pelagic, demersal, or benthic biota at or near the disposal
site when these changes can be attributed to the effects of
materials disposed of at the site.
• Accumulation of material constituents (including, without
limitation, human pathogens) in marine biota at or near the
site.
EPA has established impact categories (Section 226.lOc) in its Ocean
Dumping Regulations which specify impacts detected by site monitoring which
dictates modifications in use of the disposal site:
(1) Impact Category I: The effects of activities at the disposal
site shall be categorized in Impact Category I when one or more of
the following conditions is present and can reasonably be attributed
to ocean dumping activities: (i) There is identifiable progressive
movement or accumulation (in detectable concentrations above the
normal ambient values) of any waste or waste constituent from the
disposal site within 12 nmi of any shoreline, marine sanctuary
designated under Title III of the Act, or critical area designated
under Section 102 (c) of the Act. (ii) The biota, sediments, or
water column of the disposal site, or any area outside the disposal
site where any waste or waste constituent from the disposal site is
present in detectable concentrations above the normal ambient
values, are adversely affected by the toxicity of such waste or
waste constituent to the extent that there are statistically
significant decreases in the populations of valuable commercial or
recreational species, or of specific species of biota essential to
the propagation of such species, within the disposal site and such
other area as compared to populations of the same organisms in
comparable locations outside such site and area, (iii) Solid waste
materials disposed of at the site have accumulated there, or in
areas adjacent to the site to such an extent that major uses of the
site or of the adjacent areas are significantly impaired. The
Federal or state agency responsible for regulating such uses
certifies that such significant impairment has occurred and states
in its certificate, the basis for its determination of such
impairment, (iv) There are adverse effects on the taste or odor of
valuable commercial or recreational species as a result of disposal
activities, (v) When any toxic waste, toxic waste constituent, or
toxic byproduct of waste interaction, is consistently identified in
toxic concentrations above the normal ambient values outside the
disposal site more than four hours after disposal.
(2) Impact Category II: The effects of activities at the disposal
site which are not categorized in Impact Category I shall be
categorized in Impact Category II.
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OCEAK DUMPING PERMIT PROGRAM
EPA1 s Ocean Dumping Regulations establish a program for the application,
evaluation, and issuance of ocean dumping permits. Once a site is designated
for use, permits for disposal at the site can be issued by the EPA or CE
authority having jurisdiction over the site. The Ocean Dumping Regulations
are specific about the procedures used to evaluate permit applications, and
the granting or denying of such applications. EPA and the CE evaluate permit
applications primarily to determine whether there is: (1) a demonstrated need
for ocean disposal, and that no other reasonable alternatives exist (40 CFR
227 Subpart C), and (2) compliance with the environmental impact criteria (40
CFR 227 Subpart B, D, and E).
Compliance with EPA's environmental impact criteria ensures that the
proposed waste disposal will not "unduly degrade or endanger the marine
environment" and that this disposal will not cause unacceptable adverse
effects on human health, the marine ecosystem, or other uses of the ocean.
The criteria are too lengthy to include here; however, the relevant points are
briefly summarized below:
• Prohibited Materials; High-level radioactive wastes; materials
produced for radiological, chemical, or biological warfare; unknown
materials; persistent floatable materials which interfere with other
uses of the ocean.
• Materials present as trace contaminants only; Organohalogens; mer-
cury and mercury compounds; cadmium and cadmium compounds; oil;
known or suspected carcinogens, mutagens, or teratogens.
• Trace contaminants in the liquid fraction must neither exceed the
marine water quality criteria (EPA, 1976) nor exist in toxic and
bioaccumulative forms.
• Trace contaminants must neither render edible marine organisms
unpalatable nor endanger health of humans, domestic animals,
shellfish, and wildlife.
* Bioassays on the suspended particulates or solid fractions must not
indicate occurrence of significant mortality or significant adverse
sublethal effects, including bioaccumulation due to waste dumping.
• When bioassay methods are unavailable; Maximum concentrations of
mercury and cadmium apply; organohalogen concentrations must be less
than is known to be toxic to organisms; oils in the waste must not
produce a visible sheen on the water.
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Six types of ocean dumping permits may be issued: (1) Interim, (2)
Special, (3) General, (4) Emergency, (5) Research, and (6) Incineration-at-
Sea. In the past, EPA has usually issued Interim Permits. These permits are
valid for 1 year, maximum. They are issued when the permittee has not
demonstrated compliance of the waste with the environmental impact criteria,
but can demonstrate that the need for ocean disposal is of greater
significance to the public interest than the possible adverse environmental
impacts. Moreover, Interim Permits cannot be issued to applicants who were
not issued permits before April 23, 1978. Holders of Interim Permits must
have a compliance schedule which will demonstrate either complete phaseout of
ocean dumping or compliance with the environmental impact criteria by December
31, 1981. After that date, EPA will not issue Interim Permits and ocean
disposal of harmful wastes will cease. No present permittees at the Acid Site
hold Interim Permits.
Special Permits (issued when the applicant demonstrates a need for ocean
disposal and when wastes comply with the environmental impact criteria) may be
issued for a maximum of 3 years. Holders of Special Permits are not subject
to the 1981 deadline for cessation of the ocean disposal of harmful wastes, as
long as the criteria governing such permits continue to be met. Some
industrial permittees and all CE permittees have been granted Special Permits.
NL Industries and Allied Chemical each hold Special Permits for use of the
Acid Site.
General Permits are issued for ocean disposal of materials which will have
minimal adverse effects on the environment. Examples of materials covered by
currently effective General Permits are human remains or ashes for burial at
sea, target vessels for ordnance testing, and derelict vessels transported for
scuttling.
Emergency Permits may be issued for ocean disposal of materials which are
unacceptably risky to human health and for which there are no other reasonable
disposal techniques. Emergency Permit requests are considered individually by
EPA Headquarters on the bases of the waste's characteristics and the safest
means for its disposal.
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Research Permits may be issued for releasing material into the ocean as
part of a research project, when the scientific merit of the project outweighs
any potential adverse effects. EPA designates the disposal site(s) to be used
by Research Permit holders on the basis of the nature of the study project.
Incineration-at-Sea Permits are either Research, Interim, or Special
permits. Currently effective Incineration-at-Sea permits are Special Permits,
issued for disposal of materials at the New York Bight Wood Incineration Site.
As Special Permits, they are issued for a maximum period of 3 years. Burning
at the Wood Site is conducted under specified weather conditions and the ash
is transported back to shore and used as landfill.
INTERNATIONAL CONSIDERATIONS
The principal international agreement governing ocean dumping is the Ocean
Dumping Convention, which became effective in August 1975 upon ratification by
15 contracting countries. The Convention is designed to control waste
disposal in the oceans, and specifies that contracting nations will regulate
disposal in the marine environment within their jurisdiction and forbid all
disposal without permits. Certain hazardous materials are prohibited (e.g.,
biological and chemical warfare agents and high-level radioactive matter).
Certain other materials (e.g., cadmium, mercury, organohalogens and their
compounds, oil, and persistent synthetic materials that float) are prohibited,
except when present as trace contaminants. Other materials, such as arsenic,
lead, copper, zinc, cyanide, fluoride, organosilicon, and pesticides, while
not prohibited from ocean disposal, require special care. Permits are
required for ocean disposal of materials not specifically prohibited. The
nature and quantities of all waste material, and the circumstances of
disposal, must be reported periodically to the Intergovernmental Maritime
Consultative Organization (IMCO), which is responsible for administration of
the Convention.
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Chapter 2
ALTERNATIVES INCLUDING THE PROPOSED ACTION
The proposed action is to designate the New York Bight Acid
Waste Disposal Site for continued use. Thirty years of
studies on the effects of acid wastes disposed at the site
have not produced evidence of any adverse, long-term effects
on the site environment. Alternative sites (Figure 2-1) were
considered but rejected because there would be no
environmental benefits and barging costs to the waste
generators and monitoring costs to the Federal Government
would increase. The quality of the marine environment in the
Bight Apex would not improve if the ocean disposal of acid
wastes were moved to another site. The No-Action alternative
was rejected because there is a current need for disposal of
these wastes.
After reviewing the alternatives, EPA proposes that the interim New York
Bight Acid Waste Disposal Site be designated for continued use. The
alternatives considered were:
• No Action Alternative: The existing Acid Site Would retain its
interim designation.
• Proposed Action: Designate the existing Acid Site.
• Use of Other Sites: Designate another, existing or new, disposal
site.
The environmental consequences of each alternative, and the economic
burdens, implications and effects of each alternative have been predicted from
analyses of available data and are discussed below. Evaluations and
comparisons of the alternatives are based upon three major considerations:
• Public Health and Safety
• Ecosystem Effects
• Economic Costs
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41° -
40° -
39° -
38' -
LONG ISLAND SOUND
LONG ISLAND ... .
1. NEW YORK BIGHT ACID
WASTE DISPOSAL SITE
2. NORTHERN AREA
3. SOUTHERN AREA
4. 106-MILE CHEMICAL
WASTE DISPOSAL SITE
DELAWARE
BAY
50
NAUTICAL MILES
75°
74°
73°
- 41°
- 40°
- 39°
- 38°
72°
Figure 2-1. The Proposed Site and the Alternative Sites
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NO-ACTION ALTERNATIVE
The No-Action Alternative would result in leaving the existing Acid Site
with an interim designation. The Ocean Dumping Regulations (Section 228.12
(a)) state that the site was "...approved for dumping the indicated materials
on an interim basis pending completion of baseline or trend assessment'surveys
and designation for continuing use or termination of use ... The sizes and use
specifications are based on historical usage and do not necessarily meet the
criteria I for site designation] stated in this Part".
Taking no action toward a final determination of the sites' status —
either continued use or termination of use - would violate the intent of
Section 102 (a) of the MPRSA since the interim sites may not comply with the
site selection criteria mandated by the MPRSA and outlined in the Ocean
Dumping Regulations. Therefore, the no action alternative has been rejected
because of the need for a decision on the fate of this site - final
designation or end of dumping.
CONTINUED USE OF THE PROPOSED SITE
This section presents a detailed summary of the projected impacts of the
proposed action, which forms the basis for comparison with the other
alternative sites considered.
The Acid Site was established in 1948 for the disposal of acid wastes
generated from industries in the New York and New Jersey areas. The site is
14.5 nmi (27 km) from the New Jersey and Long Island coasts, covers 12 nmi
2
(41 km ) and is on the Continental Shelf (Figure 2-1 #4). The boundaries of
the site are latitudes 40°16' to 40°20'N and longitudes 73°36' to 73°4G'W.
Topographically, the bottom is relatively flat, with an average depth of 25.6
m (84 ft), ranging from 22.6 m (74 ft) to 28.3 m (93 ft). Sediments are
predominantly medium to fine grained sands.
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The principal user of the site, since it was first established, has been NL
Industries, Inc., which contributes about 95 percent of the total annual
volume of waste disposed therein. The only other currently active permittee
is Allied Chemical Corporation. Du Pont-Grasselli plant released part of its
caustic wastes at this site until 1975. when their entire waste, disposal
operations were moved by EPA to the 106-Mile Site.
The effects of all wastes released into the Apex of the Bight, including
those at the Acid Site, have been extensively investigated by the NOAA-Marine
Ecosystems Analysis (MESA) Program, New York Bight Project; the NOAA-National
Marine Fisheries Service (NMFS), Sandy Hook Laboratory; and the permittees
(Appendix B, Table B-l). The site environment, history of ocean disposal, and
the important waste constituents are described in Chapter 3. Chapter 4
includes a description of the environmental consequences of acid waste
disposal at this site.
PUBLIC HEALTH AND WATER QUALITY
A winter whiting fishery and some lobster fishing are conducted near the
site. During some seasons, bluefish appear to be attracted to the area, so
there is concern that disposal of acid wastes may adversely affect these
resources; however, there has been no evidence of undesirable effects. The
wastes rapidly disperse through the water column and are neutralized within
minutes by the tremendous buffering action of sea water. Biosssays have
demonstrated that the acidity of the waste is the toxic component; neutralized
wastes have low toxicity.
There is a visible impact of one waste type; when acid-iron waatea are
released, the ferrous sulfate turns the water a distinctive green color, As
the ferrous iron oxidizes to ferric hydroxide (ruat), the eolor turni
red-brown. The waste plume is distinguishable, aa much aa 41 houra after a
disposal operation; however, there are no apparent len|-terffl effeets en the
water quality. Nonetheless, thia aeathetie impact may be reapeaaible f§*
attracting bluefish to the area. When the site wai originally eh§e@a in 194S,
it was an unproductive fishing area. Meatman (19S8) reported that the area
had become popular and, in the early part of the e@aa§n, bluefiih were
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abundant at the site and the area was heavily used by sport fishermen.
Recently (1978) charter boatmen stated that the overall effect on fishing was
harmful due to the waste plume drifting outside of the site. The net effects
of the waste plume (beneficial or adverse) have not been determined.
ECOSYSTEM
Effects of acid waste on the ecosystem are undetectable. The first
investigation of the area was made in 1948, immediately before waste disposal
operations began. Since then, studies have been periodically conducted and no
adverse long-term effects attributed to the wastes have been detected or
documented (Appendix D, Table B-l, p. B~4). The major reports for the site
are by Redfield and Walford (1951), Ketchum et al. (1958b,c), Westman (1958),
and Vaccaro et al. (1972). NL Industries (1977) has summarized these and
other studies made of the site in a document included as part of their permit
application.
Investigators have examined several environmental features of the Acid Site
which may have been affected by the waste. Concerning the impacts of the
waste on the biota, the water quality, and the sediment quality, some of the
conclusions are:
Vaccaro et al., 1972:
- "There is no indication of an increase in iron (the most abundant
waste constituent) in sediments of the acid grounds over the past
14 years.
- "Although the standing crop of zooplankton and numbers of benthic
animals were less on the acid grounds than the control area, we
have been unable to attribute these differences to acid waste.
- "A phytoplankton toxicity experiment carried out in a culture
containing a 10-4 concentration of acid waste in seawater, a
concentration four times greater than that observed in the field,
has no effect on phytoplankton growth."
Grice et al., 1973:
"..laboratory experiments ... [indicate] the mortality of
zooplankton caused by the release of acid waste is negligible on
adult copepod populations because of the very few minutes in
which lethal concentrations of low pH occur immediately behind
the barge. The iron floe which persists in the acid grounds at
great dilutions does not affect adult copepods and probably does
not affect their developmental stages."
2-5
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Wiebe et al., 1973:
"... In the laboratory tests, the principal cause of copepod
mortality appeared to be the acidity of the waste product rather
than some toxic component in the material. Thus the laboratory
experiments suggest that the mortality of zooplankton resulting
from acid waste discharge is negligible because potentially
lethal concentrations of low pH do not persist for sufficient
time to produce a noticeable effect in the field. The field
observations support this conclusion... acid-waste discharges do
not appear to have a systematic effect on zooplankton numbers or
biomass which is detectable...Longer term effects on develop-
mental stages of copepods also appear negligible since
concentrations of acid waste required to inhibit development do
not occur for sufficient time in the receiving waters."
The purpose of monitoring is to ensure that long-term adverse impacts do
not develop undetected, especially adverse impacts which are irreversible or
irretrievable. Monitoring at this site is simplified since the area is
nearshore and shallow, yet difficult because there are so many contaminant
inputs to the region (Appendix C, Tables C-l to C-9). However, the
NOAA-MESA-New York Bight Project has coordinated and generated many
investigations in the Bight, and this area is one of the best understood
oceanic regions in the world. Although effects of acid waste disposal have
not been demonstrated, the long history of site-specific studies provides an
excellent base from which any changes could be detected.
EPA and NASA have cooperated in programs to develop remote sensing
techhniques (aircraft and satellite flights) for monitoring. Recent dumpings
of acid-iron can be located to within 0.1 nmi and EPA can determine if the
operations conform to permit restrictions (Anderson and Mugler, 1978). Other
work on remote sensing of acid wastes determined that iron concentrations in
seawater can be estimated using these techniques (Lewis, 1977),
Emergency, or "short", dumping occurs when the waste carrying vsssel
releases its load before reaching the designated disposal ar«a. iinet Ehi
Acid Site is close to shore, the probability of a ghert dump is quiti lew,
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ECONOMICS
For the waste generators and the Federal Government the cost of waste
disposal at the Acid Site is low. This section examines the costs of
transportation, monitoring, surveillance, and the loss of other resources.
In October 1977, NL Industries, the primary user of the site, reported that
the estimated cost for barging to the existing site was $1.84 million per
year, equal to $2,900 per trip (estimated 640 trips). Allied Chemical has
estimated costs at about five times NL Industries cost. For 12 trips per
year, the cost is about $170,000; therefore, the estimated costs for hauling
wastes to the site (including tugs, fuel, maintenance and associated shore
facilities) are about $2 million per year for the two permittees. The effects
of inflation and increased fuel costs have not been estimated; however, NL
Industries now barges less frequently to the site. This estimate does not
include other costs associated with permit analytical requirements, reporting,
and alternative studies required by current permit conditions. Site
monitoring costs are discussed below.
Rodman (1977) reported for NL Industries that a round trip takes 12 hours;
timing is very important. There are two drawbridges between the waste loading
dock and the mouth of the harbor, and the barge can only pass at certain times
and under certain tidal conditions. If barging operations have to be
postponed, NL Industries has adequate storage facilities for temporarily
holding the wastes until barging can resume.
Monitoring costs are difficult to estimate for this site; however, the cost
to the Federal Government is low since monitoring programs are required for
the other ocean disposal sites in the Apex. Monitoring costs are spread over
all the sites. The Acid Site is within the NOAA-MESA sampling grid for trend
assessment surveys, and this grid would not change if use of the site were
discontinued. The permittees are required to conduct a summer survey each
year to evaluate the short-term effects of the waste. These surveys cost
approximately $17,000 each. The cost is lower for this nearshore, shallow
site than it would be for a site further offshore in deeper water.
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The program goal for USCG surveillance at industrial waste sites is 75% of
all dumping operations. Surveillance at the Acid Site is effective and costs
are relatively low. The site is within the normal cruising range of Coast
Guard ships and helicopters, and routine surveillance can be conducted with
only infrequent use of shipriders. Vessels assigned to surveillance missions
remain available for other, higher priority missions (e.g., rescue).
There are no documented losses of biological or mineral resources in the
Apex of the Bight due to acid waste discharges. Potential mineral resources,
e.g., sand and gravel, may be contaminated by other waste sources (dredged
material, sewage sludge) but are unaffected by acid waste. Table 2-1 lists
the economically important fish and shellfish landed from the Bight. Except
for whiting, important species are either not present at the site, not
affected by acid wastes, or become contaminated by other sources, such as
sewage sludge. A whiting fishery exists near the site in the winter. The
whiting are apparently unaffected by the waste. Bluefish appear to be
attracted to the site because of the iron floe plume in the water: "...it is
reported that some fishes tend to congregate in or near the disposal area"
(Ketchum et al., 1958b).
USE OF ALTERNATIVE EXISTING SITES
INTRODUCTION
Eight municipal and industrial waste disposal sites (aside from the
proposed site) presently exist in the mid-Atlantic area (Figure 2-2), six in
the New York Bight and two near Delaware Bay. Only the 106-Mile Chemical
Waste Disposal Site is a viable alternative.
The other interim sites were not considered as possible alternative
locations for several reasons: Only the Delaware Bay Acid Site (inactive
since March 1977) has been used for acid waste disposal. The other sites are
for the disposal of construction debris (cellar dirt), wrecks, or sewage
2-8
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TABLE 2-1. FISH AND SHELLFISH LANDINGS BY STATES - 1974
Landings
Fish
Fluke
Menhaden
Scup
Whiting
Shellfish
Lobsters
Surf Clams
Scallops
New York
000 Ib
2,487
576
3,635
1,955
731
3,951
884
$000
846
18
852
250
1,396
719
1,158
New Jersey
000 Ib
3,499
107,307
6,040
7,022
1,191
22,657
344
$000
1,153
2,735
880
587
1,916
2,948
531
Total
000 Ib
5,986
107,883
9,675
8,977
1,922
26,608
1,228
$000
1,999
2,753
1,732
837
3,312
3,667
1,689
Note: Landings are shown in round (live) weight except for clams, lobsters
(total meat), and scallops (edible meat).
Source: Adapted from NOAA-NMFS, 1977a
sludge. Combining acid wastes with other materials violates the tenet of
segregating generic wastes by disposal site. Disposal of different types of
wastes at the same site could cause problems such as:
• Synergistic interactions at sites where the wastes are not
chemically inert. The effects of the combined wastes might be worse
than the sum effects of individual materials. In 1974, EPA required
that all industrial chemical wastes dumped at the New York Sewage
Sludge Site be transported to the 106-Mile Site.
• Monitoring would be more difficult since the effects of the
individual wastes would be extremely difficult to differentiate.
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LONG ISLAND SOUND
1. DREDGED MATERIAL
2. CELLAR DIRT
3. SEWAGE SLUDGE
4. ACID WASTES
5. SEWAGE SLUDGE
6 WRECKS
7. WOOD INCINERATION
8. CHEMICAL WASTES
9. ACID WASTES
10. SEWAGE SLUDGE
LONG ISLAND
DELAWARE
BAY
50
NAUTICAL MILES
38° -
Figure 2-2. Disposal Sites in the vnid-Atlantic Area
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• Some of these interim sites have already experienced adverse impacts
due to waste disposal operations (e.g., New York Bight Sewage Sludge
Site and Delaware Bay Sewage Sludge Site); the situation could be
aggravated by increasing the load or changing the character of part
of the waste load.
• Increased traffic to the nearshore sites would increase navigational
hazards and could cause logistic difficulties in coordinating
disposal operations.
The Delaware Bay Acid Site (Figure 2-2, v9) was not considered as an
alternate site for several reasons: (1) it has been inactive since March 1977
and, when sewage sludge disposal ends at a nearby site, there will be no
anthropogenic inputs to the area, (2) the site is more distant from New York
Harbor than the 106-Mile Site, which would add to transportation costs,
logistics difficulties, and fuel requirements, and (3) if acid waste disposal
should adversely affect the benthos at a shallow site, moving the disposal
operations to another shallow, coastal site would not be logical, especially
when a very deep site (106-Mile Site) could be used.
Consequently, the other disposal sites in the mid-Atlantic region were not
considered acceptable alternative locations for acid waste disposal. Only the
106-Mile Site is considered here and compared with the Acid Site.
106-MILE CHEMICAL WASTE DISPOSAL SITE
The 106-Mile Site was established in 1965 for the disposal of industrial
wastes for which there were no suitable land-based disposal methods. It is
106 nmi (196 km) southeast of Ambrose Light, New York and 90 nmi (167 km) east
2 2
of Cape Henlopen, Delaware. The site covers 400 nmi (1,648 km ) on the
Continental Slope and Continental Rise and its boundaries are 38°40'N to
39°00'N, and 72°00'W to 72°30'W. Water depths at the site range from 1,440 m
in the topographically rugged northwest corner to 2,750 m in the relatively
flat southeast corner. An inactive munitions waste disposal site is located
within the site boundaries, and an inactive low-level radioactive waste
disposal area is 5 nmi (9 km) due south.
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NOAA assisted by other government agencies and academic institutions, has
been studying this site for several years and has published survey results in
two summary reports (NOAA, 1975; 1977), several memoranda, public hearing
testimony, and the annual report to Congress (NOAA, 1978). A private company,
under contract to the permittees, has been monitoring the site for several
years. The permittees have submitted the results of these monitoring cruises
to EPA-Region II (e.g., Hydroscience, 1978). A Draft Environmental Impact
Statement on designation of the 106-Mile Site has been issued (EPA, 1979b).
PUBLIC HEALTH AND WATER QUALITY
Waste disposal at the 106-Mile Site will not directly endanger human
health. This site is not located in a commercially or recreationally
important fishing or shell fishing area. Although NOAA resource assessment
surveys do not extend out to the site, it is known that the density of fish
eggs and larvae is low beyond the edge of the Continental Shelf. Foreign
fishermen may be near the site in the late winter to early spring, but they
usually catch highly migratory fish. The probability of migratory fish
remaining in the site and accumulating toxic levels of contaminants from the
waste is extremely unlikely.
Navigational hazards due to the use of the site are minimal. Barges can
use the Ambrose-Hudson Canyon Traffic Lane for most of the journey. The
greatest danger of collision is in the Precautionary Zone through which all
the vessel traffic for New York Harbor must pass (Figure 3-10, p. 3-22). All
waste barges will pass through this area, irrespective of any designated
disposal site.
ECOSYSTEM
The short-term effects of the waste will be similar to those observed at
the Acid Site. Long-term adverse effects are improbable, since these have not
been demonstrated for the Acid Site. The potential for adverse effects on the
indigenous biota and existing water and sediment quality, although remote, is
even less at this site because the organism density is much lower and the site
is larger and in deeper water. The natural variability of the water at the
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site, caused by the interactions of three different water masses, causes
greater changes in the biotic assemblages of the site than acid waste
disposal. Consequently, only immediate, short-term (minutes) changes can be
related to the wastes (Chapter 3).
Monitoring at a site off the Continental Shelf is much more difficult than
at a shallower, inshore site. NOAA (1977) observed:
"In the case of the 106-Mile Site, this situation [the
difficulty of measuring and predicting the effects of waste
disposal] is further complicated by the interactions of major
water masses, Shelf Water, Slope Water, and Gulf Stream
eddies. The [site] is a complex oceanographic area in which
to assess natural environmental conditions and the impact of
man's activities upon those conditions."
Long-term impacts would be nearly impossible to document, since potentially
affected animals will probably have moved out of the area, either carried by
currents (plankton) or actively swimming (nekton).
The use of a distant offshore site causes increased risks of emergencies
and short dumping. The effects of a short dump of waste materials would
depend upon the location of the dump, and particularly water depth. Since acid
wastes are liquid and are rapidly diluted after discharge, a single cargo of
dumped waste would cause local, immediate acute effects, but no long-term
effects. If emergency disposal is necessary; during inclement weather, the
effects would be mitigated by the rapid dilution caused by storm turbulence.
ECONOMICS
NL Industries estimated operating costs to barge to the 106-Mile Site at
$9.25 million per year. This is about $14,500 per trip, or about five times
more expensive than present costs. Assuming that Allied Chemical's costs also
increase five times, their annual expense would be $850,000, and the total
cost would be about $10.1 million. This estimate may be low. EPA (1978a)
estimated that the cost of hauling sewage sludge to the 106-Mile Sewage Sludge
Site would be from 6.4 to 8 times more expensive than to the 12-Mile Sludge
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Site. Assuming that a similar relationship exists for acid wastes, the cost
for hauling acid wastes to the 106-Mile Site would be from $12.8 to $16.0
million annually.
Logistically, the use of this site would be extremely difficult for the
primary waste generator. NL Industries, Inc., submitted a report (Rodman,
1977) to EPA-Region II concerning the problems of moving out to the 106-Mile
Site. The barge round trip transit time would increase from 12 to 38 hours.
Barging from the present loading dock would be unfeasible due to increased
travel time, higher probability of weather delays, the requirement to pass
through two drawbridges during certain tidal conditions, and a need for
increased temporary land storage facilities. NL Industries investigated the
possibility of building new loading facilities below the drawbridges and did
not believe that the required construction permits could be obtained,
especially since the facility would be located in a wetlands area. If the
permits were granted, the estimated capital costs would be $30 million.
The cost of monitoring the 106-Mile Site is high compared to other areas
due to the complexity of the environment and distance from shore. NOAA is
responsible for assessing long-term changes through biological monitoring. A
cost of $1 million per year has been estimated for conducting baseline
surveys, two of which have been completed (Breidenbach, 1977). The Ocean
Pulse Program, based at the National Marine Fisheries Service Laboratory at
Sandy Hook, New Jersey, monitors the entire mid-Atlantic, including the
106-Mile Site. The cost to permittees for a monitoring program is also high,
due to the site's distant location. These costs would be moderately increased
if acid wastes were released at the site; however, the bulk of the monitoring
costs are due to ship time and crew costs.
Surveillance Costs
The current Coast Guard Instruction regarding surveillance and enforcement
of ocean disposal sites (Commandant Instruction 16470.2B, dated 29 September
1976) requires 75% surveillance of chemical waste disposal operations.
Surveillance activities include a shiprider aboard the vessel to observe the
disposal operation, with random spot checking before the barge leaves port,
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and checking the vessel log for departure and arrival times. The Coast Guard
presently assigns several full-time personnel to the surveillance of disposal
activities in the Bight, including the 106-Mile Site.
Shipriders are presently the only effective on-site surveillance method for
the 106-Mile Site. In 1978, 7,247 man-hours were expended in providing
shiprider surveillance, excluding the time that shipriders were awaiting
departure due to delays caused by mechanical failures or weather and tidal
conditions (Schubert, 1979). Since the Acid Site is in the Apex of the Bight
and within the normal range of Coast Guard ships and aircraft, shipriders are
not normally used.
Surveillance of acid waste disposal activities at the 106-Mile Site would
represent a significant, additional requirement for personnel, particularly
since ML Industries barges wastes at least daily. Assuming 400 trips per year
to the site, surveillance of approximately 300 disposal operations would be
required.
Loss of Biotic or Mineral Resources
Only fluke and lobster may be present at or near the site, where they may
be affected by the waste materials. (Table 2-1 lists the most economically
important finfish and shellfish in the mid-Atlantic Bight.) Since liquid
wastes would be diluted and dispersed in the water column and not reach the
bottom at this deepwater site, stocks would not be adversely affected by
disposal operations. Almost all U.S. fishing activities are located over the
Shelf, ana would not be directly affected by the wastes. Foreign ships fish
along the edge of the Continental Shelf from Georges Bank to Cape Hatteras,
especially during the late winter and early spring; however, the site is not a
uniquely productive location for foreign fishermen, and does not obstruct
migration routes of commercially valuable species. Therefore, the probability
of fish stocks accumulating toxic levels of waste constituents is extremely
low.
Oil and gas development is possible near the site (Figure 3-9). Waste
disposal would neither interfere with drilling operations nor with oil field
development. The only navigational hazard would be due to the barge traffic
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to and from the site. To date, there has been no known lost income resulting
from existing disposal operations at the 106-Mile Site, and if acid wastes
were also released there, it does not appear that income or resources would be
adversley affected.
OVERALL COMPARISON WITH THE ACID SITE
There would not be significant adverse environmental effects from acid
waste disposal at the 106-Mile Site. Effects on public health and water
quality are minimal and effects on the ecosystem would be limited to
short-term changes. However, an increase in monitoring activities would be
required, and the probability of short dumping is greater because the site is
so distant from New York Harbor.
The economic impact of moving waste disposal to this site would be severe.
Barging costs would increase five to eight times over present levels and
barging may not be feasible for the dominant waste generator. Surveillance
requirements by the Coast Guard would increase substantially since
surveillance would be required for approximately 300 barge trips a year.
Shipriders would be required frequently, whereas they are used infrequently at
the Acid Site. If acid wastes are released at this site, the probability of
biological or mineral resource losses is low.
USE OF NEW SITES
In addition to the use of an existing interim disposal site, new sites on
or off the Continental Shelf are alternatives to disposal at the Acid Site.
The area under consideration is the New York Bight and the Continental Slope
along the eastern edge of the Bight. A feasible alternative site for ocean
disposal must meet the criteria for "selection of ocean disposal sites"
(Sections 228.5 and 228.6 of the Ocean Dumping Regulations). The criteria
require that the site must not: (1) conflict with other uses of the area, such
as resource development or commercial fisheries, and (2) endanger human health
or amenities. If possible, the site should be located within the range of the
present fleet of waste disposal vessels in order to make ocean disposal
economically feasible.
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LOCATIONS ON THE CONTINENTAL SHELF
The New York Bight is one of the busiest coastal and oceanic regions in the
world. Activities include extensive commercial shipping, fishing, shell-
fishing, recreation, resource development, and waste disposal. In selecting a
site within the Bight for ocean waste disposal, other activities in the area
must be evaluated for potential effects on disposal operations and vice versa.
In addition, adequate background environmental information on the area should
be collected, so that potential effects of waste disposal can be predicted.
Most of the survey work in the Bight has centered around existing disposal
sites; however, two candidate areas for sewage sludge disposal, the so-called
Northern and Southern Areas, have been extensively studied. These areas were
selected for study by .NOAA, partly to avoid conflict with living marine
v
resources (NOAA, 1976) and are, therefore, the most reasonable alternative
locations for acid waste disposal. Within the greater areas suggested by NOAA
for consideration, two smaller areas were studied in detail and are discussed
below.
The Northern and Southern areas are representative of the marine
environment on the Continental Shelf off New Jersey (Southern area) and Long
Island (Northern area). If another location were evaluated as an alternative
site,, the same considerations discussed below would be valid. The advantage
in considering these particular areas is that surveys have been completed and
site-specific data are available. If another location were chosen for acid
waste disposal, predisposal surveys would be required.
SOUTHERN AREA
Public Health and Water Quality
The Southern Area is adjacent to commercially exploitable shellfish
resources. Surf clams and ocean quahogs are numerous in and shoreward of this
area, and sea scallops are present, but abundance estimates were not made
(EPA, 1978a).
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Since other contaminant inputs do not exist in this area, there is a risk
(although low) that the bivalves may concentrate contaminants from the acid
wastes. Preliminary work by Pesch et al. (1977) indicated that the tissues of
sea scallops accumulated vanadium from acid wastes released by Du Pont-Edge
Moor at the Delaware Bay Acid Waste Site. However, other metals present in
high concentrations in the waste (e.g., iron, manganese, and titanium) were
not accumulated by the animals. Simpson (1979), working with other bivalves
(mussels), found that the uptake and loss of trace metals varied with the body
weight of the animal and the phase of its reproductive cycle. Additional work
is needed to establish if benthic organisms can accumulate contaminants from
these liquid wastes.
Since the site is not visited by sport fishermen due to distance from
shore, the undesireable visual effect of temporarily discolored water
resulting from the release of acid-iron wastes would not be noticed at this
site; however, if bluefish are attracted to the waste plume, the sportfishing
value would be lost. In addition, if other pelagic fish avoid the waste
plume, these pelagic fisheries could be adversely affected.
Ecosystem
The short-term effects of acid waste on the water column biota would be
similar to changes already documented for the Acid Site (i.e., minor effects
on the plankton, but no irreversible changes). As noted above, there is a
small possibility of changes in benthic populations due to waste constituents.
These changes would be simple to detect, since the site is outside the Apex of
the Bight where multiple contaminant inputs exist.
Monitoring would require an additional program since none of the existing
surveys concentrates on the area. Due to the existence of the NOAA data based
on predisposal conditions in the Southern Area, monitoring is feasible. This
site is outside the heavily contaminated Bight Apex, and there are no
contaminants from other sources. Thus detecting changes caused by waste
disposal at the site would be simplified.
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Economics
The economic consequences of moving acid waste disposal to this area are
important. Neither permittee has estimated the costs of using this area.
However, EPA (1978a) estimated that the cost of hauling sewage sludge to this
area would be 3.2 to 4 times more expensive than the cost of hauling to the
existing 12-Mile Site. Assuming that the same relationship is valid for acid
wastes, the cost for hauling acid wastes to the Southern Area would range from
$6.4 to $8 million per year. For NL Industries, logistic difficulties due to
using a more distant site (as for the 106-Mile Site), are increased. If ocean
disposal is not feasible, the company would have to find alternative treatment
methods. According to reports submitted to EPA-Region II in compliance with
previous interim permits, land-based alternatives are less environmentally
preferable and economically unfeasible for the large volumes of waste liquid
generated by NL Industries (NL Industries 1975a, 1975b, 1975c 1977;
Ryckman/Edgerly/Tomlinson and Associates, 1977).
Monitoring costs would increase at this site. The cost to the waste
generators would probably be about the same as existing costs, since the
short-term effects of the waste would be similar. NOAA, however, would be
required to establish additional surveys in the site to evaluate the long-term
biological effects of waste disposal.
Surveillance costs and difficulties would increase at this site. It is
located beyond the normal operating range of Coast Guard 82-foot and 95-foot
patrol boats and helicopters normally used for surveillance, so multiple
missions are not possible. As for the 106-Mile Site, the much higher number
of barge trips would require shipriders. The overall time would be less than
at the 106-Mile Site since the transit time is less to this site. However,
the use of shipriders for acid waste would be a new requirement for the Coast
Guard.
The possible loss of biotic resources is probably the most important cost
of using this site. As shown in Table 2-1, economically important finfish
(scup and whiting) and shellfish (lobster, surf clams, and scallops) are found
in the area. The site contains an important and established fishery resource.
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Ocean quahogs, shellfish which may be exploited in the future, are abundant in
the area (EPA, 1978a). The area is shallow so that wastes may reach the
bottom and shellfish may be contaminated. Finfish may avoid the area;
consequently, use of this site could cause a significant adverse economic
impact on these living resources. The potential economic impact c.annot be
quantified because the actual amounts of fish and shellfish taken from the
area are unknown.
Use of the Southern Area would not affect sand and gravel deposits which
could be mined in the site vicinity, since the wastes are not sufficiently
toxic to require decontamination of the mined materials. Barging operations
should not interfere with exploration and development of oil and gas
resources.
Overall Comparison with the Acid Site
The possible effects on the areas of public health and water quality and on
the ecosystem are much higher at a site in the Southern Area. Since there are
no other contaminant inputs to the area, existing resources are not adversely
affected. The possibility of acid waste constituents contaminating
economically important resources does exist. Use of this area is less
economically desirable. The transportation costs to the waste generators
would increase 3.2 to 4 times, as would both monitoring and surveillance costs
to the Federal Government.
NORTHERN AREA
Public Health and Water Quality
Minimal or no effects on public health and water quality would be expected
as a result of acid waste disposal at this site. Although surf clams, sea
scallops, and ocean quahogs are present in the vicinity, commercial
possibilities are probably less than in the Southern Area (EPA 1978a).
Aesthetically, the effects of waste disposal should be minimal, the same as in
the Southern Area.
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Ecosystem
Since the oceanographic features of the two areas are similar, effects on
the ecosystem would be similar to those in the Southern Area, i.e., short-term
effects on the water with the possibility of waste constituents accumulating
in the sediments or benthic organisms. NOAA would be required to initiate a
new long-term monitoring program in addition to those already planned for
other sites. If sewage sludge were released at the Alternative Sewage Sludge
Site '(Figure 2-2, 7f5) it would be difficult to differentiate between the
effects of acid waste and sludge contaminants.
Economics
The Northern Area is almost the same as the Southern Area as to trans-
portation costs, the logistics difficulties related to a more distant site,
and monitoring and surveillance costs. These costs would be higher for the
permittees and the Federal Government. Although the Northern Area is within
the normal distribution of surf clams, they are not abundant at the site. The
density of sea scallops is not known, but ocean quahogs are abundant, and acid
waste disposal could possibly interfere with the development of these
potentially valuable marine resources. This adverse effect would be mitigated
because the net dispersive flow appears to be offshore, away from the
Continental Shelf (EPA, 1978).
Ocean disposal at a site in the Northern Area would not interfere with
development of mineral resources. It is approximately 60 nmi (110 km)
northeast of the oil and gas lease tracts identified on the mid-Atlantic
Shelf. Acid waste disposal could not possibly interfere with petroleum
exploration or development located near the Southern Area.
Overall Comparison with the Acid Site
There are few economic resources in the Northern Area, thus it is
preferable to the Southern Area. The effects on the ecosystem would be
similar to those predicted for the Southern Area and potentially more severe
than the documented effects at the Acid Site.
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Economic considerations make use of the Southern Area much less desirable
than continued use of the Acid Site. Hauling costs for the permittees would
increase 3.2 to 4 times, thus ocean disposal may not be possible for NL
Industries, which generates the largest volume of wastes requiring ocean
disposal. Monitoring and surveillance costs to the Federal Government would
increase.
LOCATIONS OFF THE CONTINENTAL SHELF
Information on the mid-Atlantic Continental Slope and Continental Rise is
lacking (TR1GOM, 1976). The 106-Mile Site is located at the closest point to
New York Harbor beyond the Continental Shelf (Figure 2-1). Due north of the
site is the Hudson Canyon, a major migratory route for fish entering the New
York Bight. (See Chapter 3.) Waste disposal nearer the Canyon would be
environmentally unacceptable, primarily because migrating organisms could
accumulate toxic constituents of the waste, and become a potential health
hazard to humans consuming infected animals.
Little background environmental information exists for the Slope beyond the
106-Mile Site. The environment immediately southwest of the 106-Mile Site
along the Continental Slope is also unknown. Designating a site for waste
disposal in that area would require extensive baseline survey work.
There are no data indicating that the 106-Mile Site is located on or near
an especially unique portion of the Shelf. The same physical processes affect
this entire region and the benthos is fairly uniform over great horizontal
distances at these depths. Other localities, further northeast or south of
the 106-Mile Site, would add considerably to the round trip time and distance
without any clear environmental benefit. In addition, the increased travel
time increases the probability of emergencies and thus increases the
probability of short dumps.
If a site off the Shelf is used for acid waste disposal, the 106-Mile Site
is the best alternative for a number of reasons. Unlike other areas off the
mid-Atlantic Shelf, the 106-Mile Site has been studied extensively, thus
2-22
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adequate information exists for projecting effects of disposal activities.
Use of any other Continental Slope site would require extensive new survey
work to produce as much data as are presently available for the 106-Mile Site.
The site is on the portion of the Continental Slope closest to New York
Harbor, and highly accessible to potential users of the site. Finally, no
environmental advantage would be gained by choosing another off-Shelf location
over the 106-Mile Site.
SUMMARY
Several alternative locations on and off the Continental Shelf have been
evaluated as potential disposal sites. A number of features of the Acid Waste
Site make it the most desirable location among all alternatives examined:
• It conforms to the Ocean Dumping Regulations' recommendation to use
either historical sites or sites off the Continental Shelf whenever
feasible.
• It has been studied extensively for more than 30 years.
• Only minor, short-term, adverse environmental changes and no
long-term effects caused by acid waste disposal have been
demonstrated at the site.
• Moving acid waste disposal from the New York Bight Apex would not
create a measurable environmental benefit, nor would areas closed to
shellfishing be reopened.
• The site is convenient to New York Harbor.
Considering all reasonable alternatives to the proposed action, the
designation of the New York Bight Acid Waste Disposal Site for continued use
is the most favorable alternative. Although there are risks involved in this
action, the environmental risk of waste disposal at this site is considered to
be less serious than the risk of disposing of wastes at a different location
on or off the Continental Shelf (Chapter 4). If subsequent monitoring of the
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site shows that adverse effects resulting from the wastes are greater than
anticipated, EPA may discontinue or modify use of the site in accordance with
Section 228.11 of the Ocean Dumping Regulations.
Table 2-2 summarizes a comparative evaluation of the possible effects of
acid wastes at the four alternate sites and outlines the effects on three
major components: (1) public health and water quality; (2) ecosystem, and (3)
economics.
DETAILED BASIS FOR SELECTION OF THE PROPOSED SITE
Part 22S of the Ocean Dumping Regulations and Criteria describes general
and specific criteria for selection of sites to be used for ocean waste
disposal. In brief, the general criteria state that site locations will be
chosen:
• "...to minimize the interference of disposal activities
with other activities in the marine environment"
• "...[So] temporary perturbations in water quality or
other environmental conditions during initial
mixing...can be expected to be reduced to normal ambient
seawater levels or to undetectable contaminant
concentrations or effects before reaching any beach,
shoreline, marine sanctuary or known geographically
limited fishery or shellfishery."
• "[site sizes] will be limited in order to localize for
identification and control any immediate adverse impacts
and permit the implementation of effective monitoring and
surveillance programs to prevent adverse long-range
impacts."
• "EPA will, whenever feasible, designate ocean dumping
sites beyond the edge of the Continental Shelf and other
such sites that have been historically used."
The New York Bight Acid Waste Disposal Site satisfies all of the above
criteria.
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TABLE 2-2. SUMMARY EVALUATION OF ALTERNATIVE DISPOSAL SITES FOR ACID WASTES
AFFECTED COMPONENT
PUBLIC HEALTH &
WATER QUALITY
Commercial Fishing
Recreational Fishing
Navipational Hazards
Aesthetics
ECOSYSTEM
Biota
• Plankton
* Nekton
• Benthos
Water Quality
• Trace Metals
Sediment Quality
• Trace Metals
Monitoring
Short Dumping
•
NORTHERN AREA SITE
None to very slight short-
term potential effects.
No effects as commercial
stocks either do not exist
(shellfish) or are not
unique (finfish) to the
area.
No effects as the site is
beyond the normal range of
most fishermen.
Very slight potential
effects as site is further
from shore.
No effects as area is not
frequented.
Slight potential effects.
Very slight toxic effects
when waste released. None
to very slight potential
for modifying the population
structure.
Very slight potential for
uptake of waste contaminants.
Moderate potential for
modifying the population
structure or contaminant
uptake.
Slight short-term increase
of concentrations.
Slight potential for
detectable accumulation .
No difficulty in following
short-term changes.
Slight short-term effects
along the Nantucket
Navigational Lane .
NEW YORK BIGHT
ACID WASTE SITE
None to very slight short-
term potential effects.
No effects documented after
30 years of disposal activi-
ties.
Slight effects.
Very slight potential effects
as site is located over part
of a traffic lane. No
increased hazard over present
practice.
Very slight effects when waste
is released. Discolored water
does not reach shore.
Very slight effects.
Very slight toxic effects
when waste released. None
to very slight potential for
modifying the population
structure.
Very slight potential for
uptake of waste contaminants.
Very slight potential for
further changes .
Slight short-term increase
of concentrations .
Very slight potential detect-
able accumulation. Cannot
distinguish from other waste
sources.
No difficulty in following
short-term changes.
Very slight short-term
effects in the Precautionary
Zone .
SOUTHERN AREA SITE
Slight potential effects.
Slight potential for contam-
ination of exploitable
resources .
No effects as the site is
beyond the range of most
fishermen .
Slight potential effects as
site is further from shore
and potential resource
development in area.
No effects as area is not
frequented .
Slight potential effects.
Very slight toxic effects
when waste released. None
to very slight potential
for modifying the population
structure .
Very slight potential for
uptake of waste contaminants.
Moderate potential for
modifying the population
structure or contaminant
uptake.
Slight short-term increase
of concentrations .
Slight potential for
detectable accumulation.
No difficulty in following
short-term changes.
Slight short-term effects
along the Hudson Canyon
Navigational Lane .
106-MILE
CHEMICAL WASTE SITE
None to very slight short-
term potential effects.
No effects as exploitable
resources are not found
in this area.
No effects as the site is
well beyond the range of
fishermen.
Moderate potential effects
as site is much further from
shore.
No effects as area is not
frequented.
Very slight potential effects
Very slight toxic effects
when waste released. None
to very slight potential for
modifying the population
structure.
Very slight potential for
uptake of waste contaminants.
No potential for bottom
effects .
Slight short— term increase
of concentrations .
No potential for detectable
accumulation .
Very slight difficulty in
following short-term changes.
Slight short-term effects.
More probable occurrence as
site Is so far from shore".
-------
TABLE 2-2. (Continued)
AFFECTED COMPONENT
NORTHERN AREA SITE
NEW YORK BIGHT
ACID WASTE SITE
SOUTHERN AREA SITE
106-MILE
CHEMICAL WASTE SITE
Si
NS
ECONOMICS
Transportation
Costs
Logistics
Energy
Requirements
Monitoring
Surveillance
Loss of Resources
• Fisheries
* Mineral Resources
Slight to moderate increase
in effects over present
practice.
Present practice. Very
slight effects .
Moderate increase in effects
over present practice.
Moderate to severe increase
in effects over present
practice .
Moderate increase over
present practice .
Moderate difficulty due to
increased barging distance
and location of loading
facilities.
Moderate increase over
current requirements .
Increased effort as site
is further from shore.
Moderate difficulty as site
is outside range of normal
Coast Guard activities.
No loss of non-commercial
resources.
No potential resources
identified.
No increase in costs .
No difficulty over current
practices .
No increase over current
requirements.
No increased effort over
current requirements.
No difficulties as site is
well within range of normal
Coast Guard activities -
Very slight effects on recrea-
tional fishing. No loss of
commercial resources.
Resources contaminated by
other waste sources .
Moderate increase over
present practice .
Moderate difficulty due to
increased barging distance
and location of loading
facilities.
Moderate increase over
current requirements .
Increased effort as site is
further from shore.
Moderate difficulty as site
is outside range of normal
Coast Guard activities .
Slight potential loss of
commercial resources .
Very slight change of loss
of potential resources•
Large increase over present
practice .
Severe difficulty due to much
increased barging distance
and location of loading
facilities.
Large increase over current
requirements.
Substantially increased effort
as site is much further from
shore.
Moderate difficulty as site Is
well outside range of normal
Coast Guard activities.
No loss of commercial or
recreational resources.
No potential resources
identified.
-------
Eleven specific site selection criteria are presented in Section 228.6 of
the Ocean Dumping Regulations. The following eleven subsections consolidate
the information for the Acid Site and show that the site complies with the
eleven site selection criteria. Additional information is in Chapter 3
(Affected Environment) and Chapter 4 (Environmental Consequences).
GEOGRAPHICAL POSITION. DEPTH OF WATER.
BOTTOM TOPOGRAPHY AND DISTANCE FROM COAST
The New York Bight Acid Waste Site is on the Continental Shelf at the Apex
of the New York Bight. (Figure 2-1.) Its coordinates are latitudes 40°16'N
to 40°20'N and longitudes 73°36'W to 73°40'W. The water depth averages 25.6 m
(84 ft) and ranges from 22.6 to 28.3 m (74 to 93 ft). The site is approxi-
mately 15 nmi south of Long Beach, Long Island and east of Long Branch, New
Jersey.
LOCATION IN RELATION TO BREEDING. SPAWNING. NURSERY. FEEDING.
OR PASSAGE AREAS OF LIVING RESOURCES IN ADULT OR JUVENILE PHASES
All of the above activities occur throughout the entire coastal area of the
mid-Atlantic Bight. The site is not uniquely important for any species and no
stage in the life history of valuable organisms occurs primarily at or near
the Acid Site. The site is just north of the Hudson Canyon, which is an
important migratory route for some animals. However, studies have not shown
that aqueous acid wastes affect the benthos; conditions in the Canyon are
primarily affected by ocean disposal activities at other sites and shore
contaminant inputs.
LOCATION IN RELATION TO BEACHES AND OTHER AMENITY AREAS
The distance from the site to the shore precludes the possibility of danger
to beaches or other amenity areas. Swanson (1977), Manager of the NOAA-MESA -
New York Bight Project, stated that, "...we have no evidence to suggest that
waste materials from the Apex Acid Waste Dumpsite have reached shore".
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TYPES AND QUANTITIES OF WASTES PROPOSED TO BE DISPOSED OF. AND PROPOSED
METHODS OF RELEASE. INCLUDING METHODS OF "PACKING THE WASTE. IF ANY
Wastes released at the site must meet the EPA environmental impact criteria
specified in the Ocean Dumping Regulations and Criteria, Part 227 Subparts
B,D, and E. In all cases, in accordance with Part 227 Subpart C, a need for
ocean disposal must be demonstrated before issuance of a permit. At this
time, permit applications from compa ies not presently (1979) barging wastes
to the ocean are not anticipated.
All wastes expected to be released following final site designation will be
aqueous acid wastes transported by vessels. The wastes will be discharged
below the surface into the vessel's wake. None of the wastes are proposed to
be containerized or packaged in any way.
FEASIBILITY OF SURVEILLANCE AND MONITORING
Both surveillance and monitoring activities are quite simple at the site.
The site is close to shore and well within the areas regularly patrolled by
the Coast Guard with 82- and 95-ft patrol boats. The site is within the
patrol range (25 miles from shore) of the Coast Guard's HH-52A helicopter,
The New York Bight has been extensively studied by researchers from the
EPA, NOAA, universities, industries, and others. One goal of the NOAA-MESA
project is to develop waste management plans and monitoring strategies for the
Bight (MESA, 1977). The existing monitoring plan for the Acid Site is
presented in Appendix E.
DISPERSAL. HORIZONTAL TRANSPORT AND VERTICAL MIXING CHARACTERISTICS
OF THE AREA. INCLUDING PREVAILING CURRENT DIRECTION AND VELOCITY
The physical oceanographic features of thg Aeid Sits ar§ ds§eribtd in
detail in Appendixes A and B. The waste bthavier iffltnidiatsly after r§lsa§s is
discussed in Appendix D.
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Wastes from both permittees are diluted and dispersed well within the
allowable 4-hour mixing period. Even if a direct current traveled from the
site to the shore, the concentration of the most abundant waste constituent
would be well below ambient levels. One waste type forms an iron hydroxide
(rust) floe which is persistent; a colored waste plume may be detectable up to
48 hours after a disposal operation.
Surface currents in the Bight often move in an anticyclonic (clockwise)
eddy around the Bight. At the site, surface and bottom currents tend to move
in northerly and westerly directions. These directions, however, are neither
constant nor predictable, and the details of the circulation within the Apex
\
of the Bight have not been resolved.
EXISTENCE AND EFFECTS OF CURRENT AND PREVIOUS DISCHARGES
AND DUMPING IN THE AREA (INCLUDING CUMULATIVE EFFECTS)
Numerous studies have failed to detect significant, long-term, adverse
effects caused by the acid wastes at this site. Redfield and Walford's (1951)
conclusion is still valid:
"Consideration of the general rate of exchange of water
between the New York Bight and the adjacent parts of the
ocean make it extremely unlikely that the quantity of waste
discharged during more than a few days could be found in the
region at any one time. No evidence has appeared which
indicates that undesirable effects of any sort have arisen
from these waste disposal operations."
INTERFERENCE WITH SHIPPING. FISHING. RECREATION. MINERAL EXTRACTION.
DESALINATION. FISH AND SHELLFISH CULTURE. AREAS OF SPECIAL SCIENTIFIC
IMPORTANCE. AND OTHER LEGITIMATE USES OF THE OCEAN;
Mineral extraction, desalination, and fish and shellfish culture do not
occur at or near the site. The site is not located in a unique area of the
Bight and is not an area of special scientific significance other than the
evaluation of acid waste disposal. Although the site is in one of the
outbound traffic lanes from New York Harbor, the disposal operations have not
interfered with shipping. When in the traffic lane, the barge moves parallel
to it; otherwise, it moves at right angles to the traffic. In the 30 years of
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operations at the site, there has never been a collision of a waste-
discharging barge and another vessel, although a collision did occur in 1976
between a ship and a barge bound for the 106-Mile Site (P. Anderson, personal
*
communication ).
Recreational fishermen in both private and charter boats use the site.
Numerous studies have been made on the effects of acid waste disposal on
finfish of the area. The conclusions of Ketchem et al. (1958), that the waste
is nontoxic and rapidly diluted, are still valid. No deleterious effects of
waste disposal on the plankton populations have beeen demonstrated and, in
fact, some fish may be attracted to the area.
THE EXISTING WATER QUALITY AND ECOLOGY OF THE SITE AS DETERMINED
BY AVAILABLE DATA. BY TREND ASSESSMENT. OR BASELINE SURVEYS
The large numbers of surveys made at or near the site have been summarized
above, in Chapter 4, and in Appendix B. Adverse effects resulting from acid
waste disposal have not been documented.
Both NL Industries and Allied Chemical Corporation have evaluated the
influences of their respective wastes on the existing water quality of the
site (ERCO, 1978a,b). The wastes of both industries comply with the marine
water quality criteria for all constituent materials. Concerning the ecology
of the site, Swanson (1977) stated:
"Hydrated, iron oxide precipitates from acid wastes coat
suspended particles, including biota. It might be
suspected that coatings could adversely affect some membrane
transport functions. No observational evidence can be found
to indicate any effects on biota from such coatings. Surveys
of benthic populations in the immediate vicinity of the Apex
Acid Waste Dumpsite have not demonstrated an observable
impact of waste acid. Such an observation at the site would
not be expected for two reasons: first, the acid waste
materials do not accumulate in the sediments at the site; and
second, any impacts would be the sum of all activities
affecting the site, and could not be attributed to acid
wastes alone. Long-term, sublethal, toxic effects on
organisms at and near the Apex site have not been
investigated."
* P. Anderson, Chief, Marine Protection Branch, EPA, Region II, Edison N.J,
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Swanson's last statement refers to comprehensive, in situ, studies.
Vaccaro's group (Vaccaro et al., 1972; Grice et al., 1973; Wiebe et al., 1973)
did investigate chronic effects of acid waste in the laboratory and concluded
that biologically significant effects did not occur. If adverse effects due
to waste disposal are detected, the Ocean Dumping Regulations state that
appropriate mitigating measures must be taken ranging from reducing the
discharge rate, frequency of dumping, or annual volume to relocating the
disposal operations or prohibiting ocean disposal (40 CFR 228.11).
POTENTIAL FOR THE DEVELOPMENT OR RECRUITMENT OF NUISANCE SPECIES
IN THE DISPOSAL SITE
Based on 31 years of disposal, it can be stated that acid waste does not
promote or attract nuisance species in the area. Extensive phytoplankton
blooms in the Bight which cause adverse effects, usually result from an excess
of nutrients combined with anomalous physical conditions (Sharp, 1976). Acid
wastes do not contain constituents which promote phytoplankton growth.
EXISTENCE AT. OR IN CLOSE PROXIMITY TO. THE SITE OF ANY SIGNIFICANT
NATURAL OR CULTURAL FEATURES OF HISTORICAL IMPORTANCE
No such features are known to exist at or near the site. The site is
sufficiently distant from shore so that wastes do not affect state or national
parks or beaches.
CONCLUSIONS AND PROPOSED ACTIONS
EPA has determined that the interim Acid Waste Disposal Site should be
placed in Impact Category II. This area is the most preferred location for
disposal of some acid wastes generated in the Northeastern United States.
All future use of the Acid Site for acid waste disposal must comply with
the EPA Ocean Dumping Regulations and Criteria, a requirement which brings
disposal into compliance with the MPRSA and the Ocean Dumping Convention. EPA
2-31
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determines compliance with the Regulations on an individual basis during
evaluation of applications for disposal permits. General guidelines for
determining the acceptability of wastes proposed for release at the Acid Site
follow.
TYPES OF WASTES
Waste materials similar to those previously released at the site are
acceptable since significant adverse environmental effects from these wastes
have not been demonstrated. If adverse effects are observed in later
monitoring, disposal must be altered (reduced or stopped) until such effects
cease (Ocean Dumping Regulations, Section 228.11). Provisionally, industrial
wastes with the following characteristics may be released at the site:
• Aqueous acid wastes with low solid phase content
• Neutrally buoyant or slightly denser than seawater
• Low toxicity (after neutralization) to representative marine
organisms
• Containing no materials prohibited by the MPRSA
• Limiting permissible concentration for all waste constituents will
not be exceeded outside the disposal site during initial mixing (4
hours) nor will it be exceeded anywhere in the environment after
initial mixing.
Essentially, these are liquid wastes which comply with the Ocean Dumping
Regulations concerning environmental impact, need for ocean disposal, and
impact on aesthetic, recreational, economic, and other uses of the ocean.
WASTE LOADINGS
Since cumulative adverse effects of past waste loading have not been
demonstrated at the site, no upper limit can be assigned beyond which adverse
effects could occur. The maximal historical input, about 5.45 million tonnes
of acid wastes in 1963, did not cause observable adverse effects. It is
certain that historical average volumes are acceptable (about 2.3 million
tonnes per year). Existing (1979) permits allow a maximum of 2.2 million
tonnes annually to be released at the site. However, the total annual input
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is not the critical element in evaluating the effects of waste loading at the
site; rather, an individual barge Toad is important because the waste
constituents do not accumulate, but are dispersed below detectable levels by
currents. The rate of release of each waste load must not be greater than the
ability of the water to dilute it to acceptable levels within a short period
of time. Compliance with Section 227.8 of the Ocean Dumping Regulations
(limiting permissible concentration) should ensure that the marine environment
will not be adversely or irreversibly affected.
The total assimilative capacity of the site or area is not known for these
wastes since long-term adverse effects have not been demonstrated. Since the
current patterns in the Bight are highly complex and have large, unpredictable
variations, even the short-term (days) transport of the waste cannot be
predicted. Therefore, estimating maximal seasonal or annual waste loadings is
not possible at this time. Each waste proposed to be released must be
evaluated individually and relative to other waste inputs, for dispersal
characteristics and input of toxic elements to the Apex environment. Waste
loadings above the present level may be permitted as long as the site is
carefully monitored for adverse effects. However, the amount of material
released in each barge load must not be greater than can be reduced to
acceptable levels by dispersal and dilution at the site. The size of barge
loads and release rates of materials at the site are established by EPA to
satisfy this objective.
DISPOSAL METHODS
Present disposal techniques are acceptable and will be required for future
permittees. The wastes are transported to the site in specially constructed
rubber-lined barges. Wastes are discharged from 30-cm diameter underwater
ports at a specified rate while the barge is under way (5 to 7 kn). The
turbulence created by the wake of the barge causes immediate dilution of the
waste (from 1:250 to 1:1,800). The acid is neutralized by the buffering
action of seawater; pH changes are detected only occasionally behind the barge
and rarely exceed 0.2 pH units below ambient conditions, even a few minutes
after discharge. This method (or another method that maximizes initial
dilution upon discharge) will be required for all future disposal.
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DISPOSAL SCHEDULES
Since only two companies are using the site, there have not been any
scheduling problems. Allied Chemical Corporation makes 12 to 18 trips per
year to the site, while NL Industries barges at most twice (usually once) a
day. Only one barge will be allowed in the site during a 4-hour period. This
requirement prevents additional hazards from shipping and the possibility that
conditions within the site would still show the influences of the previous
dump.
SPECIAL CONDITIONS
Current permits have ten special conditions, which will remain part of
future permits issued for waste disposal at the Acid Site:
• Special Condition 1 is the time period the permit is in force.
Current permittees are:
NL Industries, Inc., April 10, 1979 to April 9, 1981
Allied Chemical Corp., April 10, 1979 to April 9, 1981
• Special Condition 2 is a description of the material to be
transported for ocean dumping. This condition requires quarterly
reports from both the waste generator and waste transporter on the
volumes of waste delivered or transported. Allowable volumes (1979)
are:
NL Industries - not to exceed 2,147,000 tonnes per year
(2,370,000 wet tons) or 2,721,000 tonnes (3,000,000 wet
tons) during the term of the permit of liquid sulfuric
acid and gangue solids slurry.
Allied Chemical - 51,700 tonnes (57,000 wet tons) per year
of by-product hydrochloric acid generated in the
manufacture of fluorocarbons.
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• Special Condition 3 specifies the disposal site. Present permittees
both release wastes at the New York Bight Acid Waste Disposal Site.
• Special Condition 4 lists the barges to be used and requires that
navigational overlays of the dump vessel's trackline during any
disposal operation be submitted to the Coast Guard. The waste
transporter must notify the Captain of the Port, U.S. Coast Guard,
of his departure time from the port and the time of actual
discharge. Discharge rates are also indicated. Current barges used
are:
NL Industries: MORAN 102 (633,000 gal capacity)
MORAN 108 (990,000 gal capacity)
Allied Chemical: AC-5 (456,000 gal capacity)
Discharge rates are presently:
NL Industries: 100,000 gal/nmi
(378,500 1/nmi)
Allied Chemical: 12,000 gal/nmi
(45,400 1/nmi)
• Special Condition 5 specifies the waste constituents to be
monitored, the approved analytical procedures, and some requirements
for laboratory quality control practices. Samples are taken monthly
for analyses.
• Special Condition 6 requires the continuation of the EPA approved
monitoring program to determine the short-term environmental impacts
of the ocean disposal of acid waste. Details of the monitoring
program are in Appendix E.
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Special Condition 7 pertains to the implementation of alternative
disposal methods. Both current permittees have submitted reports to
demonstrate that their respective wastes are in compliance with 40
CFR 227. This condition requires further research and evaluation of
alternative disposal methods with the objective of ending ocean
disposal. The conditions in the current permits are:
NL Industries:
(1) After publication of the proposed national effluent
guidelines for the titanium dioxide industry, the company
will submit a plan committing it to cease ocean dumping
within 18 months of promulgation of final guidelines.
(2) Evaluate the feasibility of three process changes:
(a) Chloride process
(b) Ishihara process (ammonia neutralization)
(c) Malazsian Titanium Corp., process
(3) For the acid wastes, report amounts produced, amounts
discharged to municipal treatment plants, amount recycled,
and amounts sold.
(4) Plan and implement a land-based disposal method for the
insoluble gangue and ore slurry. Anticipated cessation of
the ocean dumping of this material is June 30, 1981.
(5) Continue research and development on alternative
land-based disposal techniques for the acid phase of the
waste.
Allied Chemical:
(1) Submit a detailed report prepared by an independent
consultant evaluating economic and environmental effects
of several alternative technologies recently (1977-1978)
studied by the company.
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(2) Report amounts of by-product acid produced and amounts
sold.
(3) Continue research and development in alternative
land-based disposal techniques.
The EPA has required the waste generators to evaluate several
land-based alternatives in previous permit requirements. To date,
these alternative disposal methods have not been economically and/or
technically feasible, nor would they have provided significant
environmental protection. Recycling or upgrading and selling the
wastes is done to the maximum possible extent. Listed below are the
alternatives to ocean disposal considered by the permittees:
NL Industries:
(1) Neutralize the acid waste with caustic soda, landfill
sludge solids, and discharge effluent into the Raritan
River.
(2) Neutralize the acid waste producing usable by-products and
landfill sludge solids.
(3) Change to the chloride process to produce less waste.
(4) Neutralize the acid waste before ocean disposal.
Allied Chemical:
(1) Neutralize the acid waste, landfill sludge solids, and
discharge clarified effluent to Newark Bay.
(2) Upgrade and sell a portion of the acid waste, and
neutralize the excess-producing sludge for landfill and a
clarified effluent.
(3) Convert by-product hydrochloric acid to chlorine using the
Kel-chlor process, which produces a less toxic waste.
(4) Neutralize the acid waste before ocean disposal.
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• Special Condition 8 details procedures for notifying the U.S. Coast
Guard that dumping is to occur. This notification is required to
facilitate USCG surveillance of disposal operations.
• Special Condition 9 details information relative to correspondence
and reports required by the special and general conditions of the
permit.
• Special Condition 10 specifies the liabilities for compliance
related to the special conditions of the permit as applicable to the
waste generator, waste transporter, or both.
These special conditions will continue to be part of all permits authorized
for wastes to be released at the Acid Site.
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Chapter 3
AFFECTED ENVIRONMENT
The environmental characteristics of the proposed New York
Bight Acid Waste Disposal Site and three alternative sites
(106-Mile Chemical Waste, Northern Area, and Southern Area)
were assessed in terms of oceanographic features (physical,
geological, chemical, and biological), the history of waste
disposal at the sites, the effects of wastes at the sites,
and other activities near the sites which may be affected by
waste disposal. The proposed site, located nearshore at the
Apex of the New York Bight, has been used since 1948 with no
adverse effects on the environment or on activities in the
area. The 106-Mile Site, located beyond the Continental
Shelf in deep water, has been used since 1961 primarily for
aqueous chemical waste disposal with no detected adverse
effects. The Northern and Southern areas, located in shallow
water near Hudson Canyon with oceanographic features similar
to the proposed site, have never been used for waste
disposal. The Acid Site is preferred for designation because
of (1) the greater distance to the 106-Mile site and the
difficulty of detecting effects in deep water, (2) the
absence of other contaminant inputs and the additional
expense of surveillance and monitoring at the Northern and
Southern sites, and (3) the lack of adverse effects at the
proposed New York Bight Acid Waste Disposal Site.
PROPOSED SITE - NEW YORK BIGHT ACID WASTE SITE
SITE ENVIRONMENT
The Acid Site (Figure 3-1) is not unique when compared with the rest of the
New York Bight Apex. Physical processes operate over broad areas, the
chemical and biological features of the water being nearly uniform over the
entire Apex. The sediments and associated biota in the Apex and at the site
are typical of the sandy bottom assemblages found throughout the mid-Atlantic
Bight. Although anthropogenic inputs (dredged material, sewage sludge, and
cellar dirt) have extensively modified the sediments in some areas, acid
waste, which is liquid, does not appear to affect the bottom. (See Appendix B
for details.)
3-1
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jr. BROOKLYN ..>£-. .,
SANDY HOOK - ROCKAWAY POINT TRANSECT
DREDGED ,-.
MATERIAL |
SITE
U—SEWAGE SLUDGE
SITE
ACID WASTES SITE
—^BIGHT APEX LIMITS
WOOD INCINERATION SITE
10
NAUTICAL MILES
Figure 3-1. Location of New York Bight Acid Waste Disposal Site
3-2
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PHYSICAL CONDITIONS
The physical characteristics of the New York Bight are complex. Seasonal
patterns of temperature, salinity, insolation, ana river runoff are
complicated by strong meteorological events and intrusions of Slope Water
(Bowman and Wunderlich, 1977). The hydrography of the New York Bight exhibits
clear seasonal cycles in temperature, salinity, and density structures. Two
distinct oceanographic regimes, with short transition periods between them,
prevail during an annual cycle. Early winter storm mixing and rapid cooling
at the surface create well-mixed, unstratified water. A moderate
stratification develops in the early spring and intensifies through the summer
(Charnell and Hansen, 1974). The rapid formation of the seasonal thermocline
divides the water into an upper and lower layer. Bottom waters retain their
characteristics with little modification until storms break up the thermocline
in late autumn.
The major feature of Bight circulation is a slow flow to the soutnwest over
most of the outer Continental Shelf; an anticyclonic (clockwise) eddy is often
present in the inner Bight. Exchange circulation, characterized by seaward
surface flow of estuarine waters and landward flow of bottom waters, occurs
through the Sandy Hook-Rockaway Point Transect. All of these features can be
masked by stronger but variable wind-driven currents on a day-to-day basis,
and may be drastically altered for periods of several weeks. Alterations are
more common during the summer, when there may be sustained periods of strong
southerly winds (Hansen, 1977).
GEOLOGICAL CONDITIONS
The Continental Shelf surface of the New York Bight is a vast, sandy plain,
underlain by clay (Emery and Schlee, 1963; Milliman et al., 1972). While sand
is the most abundant textural component on the Shelf, significant deposits of
gravel and mud are also present. Sediments at the Acid Site are 96 to 96%
sand and gravel with the remainder being silt. The site is at the edge of the
Hudson Canyon where the predominant sediments are silts and clays.
3-3
-------
Suspended particulate matter (SPM) includes fine material from natural and
man-made sources. SPM may be transported for some distance by waves and
i
currents before sinking to the bottom, and may be resuspended by bottom
currents and transported to another area. SPM can cause several adverse
environmental effects: higher levels of this material can increase turbidity,
in turn decreasing the depth light penetrates in water, thereby limiting the
depth at which plants can photosynthesize and the amount of primary production
in the ocean. Suspended particulates can be toxic or can bind or adsorb toxic
materials which are eventually carried to the bottom. While suspended in
water or lying on the bottom, the toxic material can be consumed by marine
organisms.
The Acid Site has concentrations of SPM typical of ,other Apex areas and
higher than areas further offshore. Acid-iron waste does contribute to the
elevated levels of SPM in the Apex; the ferric hydroxide floe forming after
waste release remains in suspension for many hours'. Additional significant
sources of SPM to the Apex are material from other ocean disposal sites
(Dredge Material, Cellar Dirt, and Sewage Sludge Sites), atmospheric fallout,
and outflow from New York Harbor through the Sandy Hook-Rockaway Point
Transect. SPM, however, is not a major environmental problem in the Bight.
After considering the effects from all sources, Pararas-Carayannis (1973)
concluded that, "turbidity associated with ocean dumping does not appear to
have an adverse lasting effect on the sediment and water quality of the
Bight."
CHEMICAL CONDITIONS
The coastal metropolitan area is the primary source of heavy metals
entering the New York Bight (Benninger et al. , 1975; Carmody et al., 1973).
The concentrations of dissolved heavy metals in the water of the New York
Bight vary seasonally.. Background (natural) concentrations however, are
generally higher than those reported for the open ocean (Brewer, 1975). Heavy
m tal concentrations in bottom sediments are not uniformly distributed
throughout the Apex; elevated levels of metals in .the sediments of the Bight
are associated with Hudson Canyon, and the Dredged Material and Sewage Sludge
Sites. Levels of iron (the most abundant waste constituent) were similar at
3-4
-------
the Acid Site and a control area, but were half the level oi metals in samples
from the Hudson Canyon. Although some material may reach tne bottom during
unstratified (winter) conditions, there is no indication of a Duildup of
contaminants from acid waste in the sediments.
Surface values of dissolved oxygen are usually at or near saturation
levels. Below the seasonal thermocline, saturation may fall to 30X» in the
vicinity of the Sewage Sludge Site (O'Connor et al., 1977). There is no
indication of abnormally depressed oxygen levels near the Acid Site. Levels
of trace metals in the water are higher than in samples from the outer Bight,
but there are no indications of consistently higher levels near the ocean
disposal sites (Segar and Contillo, 1976). Acid waste disposal only causes
short-term perturbations in the water. Since the,flushing time for the entire
Apex of the Bight is 6 to 14 days, the waste is being continually diluted and
transported from the region.
Particulate organic carbon, which may act as a transport agent for toxic
substances, has the highest concentrations near areas of wastewater discharge
t
(outfalls) and the Sewage Sludge and Dredged Material Sites. No comprehensive
studies of chlorinated hydrocarbons in the New York Bight have been made, but
dredged material and sewage sludge disposal are probably the major sources of
these materials (EPA, March 25, 1975; Raytheon, 1975a, 1975b; West et al.,
1976).
BIOLOGICAL CONDITIONS
During most of the year, the ranges of daily phytoplankton production for
inshore and offshore areas of the New York Bight do not differ significantly
from one another. Total annual production, however, is higher in coastal
waters.
Phytoplankton populations are dominated by diatoms in cold months, and by
chlorophytes during warm months, in the Hudson River estuary and Apex, and by
diatoms year-round in the outer Bight. Zooplankton populations are dominated
by copepods and larvae of vertebrates and invertebrates (summer only) in the
estuary, and by copepods in the outer Bight. However, the high degree of
3-5
-------
spatial and temporal variation inherent in plankton populations makes studies
of their abundance, composition, and distribution extremely difficult. Even
though plankton have been studied for about 75 years, the data are insuf-
ficient to assess the effects of man's activities on plankton populations in
the Bight (Malone, 1977).
Many finfish of commercial and recreational importance are found in the New
York Bight. Their diversity and abundance are due to the geographical
location of the Bight which is the northern limit of tropical and subtropical
migrants and the southern limit of boreal migrants (Grosslein, 1976). Some
species are found inshore, others offshore, and some migrate from inshore to
offshore. However, because of wide seasonal fluctuations in the Bight
(especially temperature, which ranges from 2 C in the winter to 25 C in the
summer), the important fish species are migratory, and not unique to the Apex
of the Bight.
There is a rich mixture of species in the Bight, with each species
occupying wide areas over the Shelf. Eggs, larval stages, and immature forms
can be found all year round throughout the area. Since spawning and larval
growth usually spreads over a broad geographic area, it is difficult to assess
man's effects on the stock. Grosslein indicated that there are no Shelf areas
free from potential changes induced by waste disposal activities.
Commercial fishing activities are minor around the Acid Site. A seasonal
whiting fishery exists north of the site along the edge of the Hudson Shelf
Valley during the winter, and lobster are taken inshore from the site. Most
of the Bight Apex is closed to shellfishing because of contamination. For
commercially important shellfish, some species are evenly distributed over the
Bight, while others, such as the sea scallop, show a more patchy distribution
(Figure 3-2) .
Tht inshore benthic fauna are dominated by organisms characteristic of a
high-energy coastal marine environment; bivalves Tellina agilis and Spisula
solidissima, and the sand dollar, Echinarachnus partita (Pearce, 1972). Benthic
3-6
-------
74'
73s u
41 -
1. NEW YORK BIGHT ACID SITE
2. NORTHERN AREA
3. SOUTHERN AREA
4. 106-MILE SITE
40'
39
72"
38-
I. ':!. I OCEAN QUAHOC
SEA SCALLOP
SURF CLAM
CLOSED TO SHELLFISHING
100
41-
40-
39:
381
73-
Figure 3-2.
Distribution of Surf Clams, Ocean Quahogs, and Sea Scallops in
the New York Bight (NOAA-NMFS, 1974c)
J-7
-------
populations in the Bight are not static and substantial annual changes occur
due to natural causes. The benthic fauna change from a sand bottom assemblage
to silty-sand and then silty-clay fauna further offshore in the Bight'
(Figure 3-3).
WASTE DISPOSAL AT THE NEW YORK BIGHT ACID WASTE DISPOSAL SITE
The Acid Site was estaolished in 1948 for disposal of aqueous waste
produced by industries in the New Jersey and New York areas. Tne site
location was specifically chosen to avoid conflict with fisheries. The
Interim Site, established by EPA in 1973, is bounded by 40°16'N to 40°2U'N and
73°36'W to 73°40'W. Waste disposal at the site is discussed in detail in
Appendix D, and summarized below.
RECENT WASTE DISPOSAL ACTIVITIES
Two permittees: NL Industries, Inc., and Allied Cnemical Corp. are now
(.1979) using the Acid Site. NL Industries liquid waste material consists of
approximately 8.5% (by weignt) sulfuric acid (H..SO,) and 10* (.by weignt)
ferrous sulfate (FeSO,) dissolved in fresh water. Insoluble materials (e.g.,
silica and unrecovered titanium dioxide) are present in the waste. when the
waste is discharged, the ferrous sulfate colors the water light green. The
barge's wake then turns brown as the ferrous iron is oxidized to form ferric
Hydroxide (rust) . NL Industries' waste represented 97% of the total amount
discharged at the site between 1975 and 1978.
Allied Chemical's waste material consists of approximately 30/o by volume
hydrochloric acid (HC1) , 2/» by volume hydrofluoric acid (HF) , and trace
constituents in aqueous solution. Allied Chemical wastes represented 3£ of
tne total material released at the Acid Site between 1975 and 1978.
WASTE CHARACTERISTICS
Several studies have shown that the acid wastes do not remain together as a
cohesive mass but are diluted rapidly after discharge. Redfield and Walford
(1*51) reported that the maximum volume of water having an acid reaction was
3-8
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LONG ISLAND SOUND ^
1. NEW YORK BIGHT ACID SITE
2. NORTHERN AREA
3. SOUTHERN AREA
4. 106-MILE SITE
LONG ISLAND ,, .
SAND FAUNA
SILTY-SAND FAUNA
SILTY-CLAY FAUNA
DELAWARE £
BAY
0 50 100
NAUTICAL MILES
38° -
75:
Figure 3-3. Benthic Faunal Types in the mid-Atlantic Bight (Pratt, 1973)
-------
162,000 m (640 m long, 23 m wide, and 11 m deep); the acid was neutralized
within 3-1/2 minutes after discharge. They calculated that at discharge, the
sulfuric acid would be immediately diluted to 0.02 ug/1 and the seawater pH
would not fall below 4.5. The actual pH depression observed 2 minutes after
discharge was only 1.3 pH units (from 8.2 to 6.9).
Trace metals in acid waste are insignificant sources of contaminants to the
Bight Apex. In all cases, the acid wastes contribute less than 1% of the
total input and usually much less than the input from atmospheric fallout
(Figure 3-4).
EFFECT ON ORGANISMS
Before ocean dumping was regulated by the EPA, numerous laboratory and
field toxicity studies had been performed on the wastes dumped at the Acid
Site. Observations of minor effects were reported by Redfield and Walford
(1951), PHSSEC (1960), Ketchum et al. (1958a,b), Vaccaro et al. (1972), Wiebe
et al. (1973), Grice et al. (1973), and Gibson (1973). In contrast, the
NMFS-Sandy Hook Laboratory (1972) reported severe effects due to acid waste
disposal; however, the NMFS method and conclusions were criticized by Buzas et
al. (1972).
A variety of phytoplankters and zooplankters have been collected in the
wake of an acid waste discharge. Animals may be immobilized immediately after
disposal, but recover quickly when the waste is diluted with an equal volume
of seawater. The gastrointestinal tracts of copepods and ctenophores
collected at the site after a discharge were full of iron particles from the
waste, but the animals did not appear to show ill effects.
Laboratory work indicated that phytoplankton were unaffected by a concen-
tration of acid waste four times higher than concentrations observed in the
field. Zooplankton were chronically affected by concentrations of one part
waste in 10,000 parts seawater. Reproduction was impaired and development
slowed over an 18-day period. These results, however, are not biologically
important since this concentration of waste only persists for a few minutes
after disposal. When the toxicity of neutralized acid waste and the toxicity
3-10
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NEW JERSEY COASTAL
LONG ISLAND COASTAL
SEWAGE SLUDGE
ACID WASTE
ATMOSPHERE
MASS LOADING BY SOURCE - ALL METALS
CHROMIUM (5.6 METRIC TONS/DAY)
LONG ISLAND
NEW JERSEY
ACID WASTE
LEAD (12.6 METRIC TONS/DAY)
NEW JERSEY
COPPER (13.8 METRIC TONS/DAY)
LONG ISLAND
NEW JERSEY
ATMOSPHERE
SEWAGE SLUDGE
ACID WASTE
ZINC (32.3 METRIC TONS/DAY)
NEW JERSEY/LONG ISLAND
SEWAGE SLUDGE
ACID WASTE
\
ATMOSPHERE
ALL VALUES OBTAINED IN 1973 (ADAPTED FROM MUELLER et al., 1976)
ACID WASTE
ATMOSPHERE
Figure 3-4. Inputs of Metals to the New York Bight
(Adapted from Mueller et al., 1976)
3-11
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of the pH change were determined, the pH change appeared to cause lethal
effects rather than the toxic elements in the waste. Neutralized acid waste
was not toxic to test organisms.
When the site was first established (.1948), there was controversy over
possible effects on the migratory fish in the New York Bight. NL Industries
sponsored the first comprehensive studies of the effects of acid-iron waste
which concluded (Redfield and Walford, 1931), that there was no conflict
between the waste disposal operations and sportfishing activities in the Bight
Apex. Since this work, Westman has periodically surveyed the site and other
fishing areas in the Bight (Westman, 1958, 1967, 1969; Westman et al., 1961),
and concluded that bluefish and yellowfin tuna were attracted to the site, and
that an active pelagic fishery had begun in the area. He did not observe
adverse effects caused by the waste dispossal.
The waste does not appear to be toxic to the bottom-dwelling animals
(benthos). The site supports a typical sand-bottom community; the biomass and
species diversity are comparable to a control area (Vaccaro et al., 1972)
although the number of animals is significantly less. Other investigators
(Westman, 1967, 1969; NMFS, 1972) have reported anomalous benthic conditions
at the site. Recent samples (Pearce et al., 1976a,b, 1977) showed that there
were wide natural variations at stations in and around the site. Such
variability is common for sand-bottom assemblages of animals.
CONCURRENT AND FUTURE STUDIES
Scientific Investigations of the Area
The NOAA-MESA program is responsible for identifying and measuring the
impact of man on the marine environment of the New York Bight and its
resources. This program began in 1973 and is scheduled to end in 1981.
After that date, a smaller monitoring program will be maintained to provide
the data necessary for management decisions about use of the resources in the
Bight. The MESA project has sponsored and conducted numerous investigations
of all the oceanographic features of the Bight; these data provided much of
the information used in the EIS.
3-12
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The Sandy Hook Laboratory (SHL) of the National Marine Fisheries Service
(NMFS) conducts continuous studies of the area, primarily with respect to
man's impact on commercial fish and shellfish resources. Their Ocean Pulse
Program is designed to monitor and assess the health of the ocean's living
resources on the Continental Shelf of the Northwest Atlantic Ocean. This
program includes the study of effects of pollutants on important marine
species.
Area-Wide Planning
The Interstate Sanitation Commission (ISC) conducts research, monitoring,
and regulation activities in the New York-New Jersey area. They are primarily
concerned with monitoring water quality and verifying compliance with existing
interstate regulations by sanitary waste dischargers. The ISC is developing a
combined management plan for municipal waste and have begun to monitor air
quality in the New York Bight. Although this work is not directly pertinent
to the Acid Site, it is close enough to the site to produce important
information for evaluating effects of acid wastes on the marine environment.
Monitoring
The EPA Region 11 requires permittees to monitor the respective sites to
determine if disposal operations have a short-term adverse impact. Monitoring
surveys are made at the Acid Site once a year (1979) and at the Sewage Sludge
Site daily during the summer. Monitoring plans have been developed for the
Cellar Dirt Site and are being developed for the Dredged Material Sites.
OTHER ACTIVITIES IN THE SITE VICINITY
COMMERCIAL FISHERIES
Extensive fin- and shellfishing activities are conducted in the New York
Bight. Most of the finfish grounds lie over the inner Continental Shelf or
near the edge of the Shelf. Most species of shellfish are found throughout
the Bight, while others, such as lobster, are most abundant nearshore in the
Hudson Canyon or at the edge of the Continental Shelf.
3-13
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DOMESTIC FISHERIES
Table 3-1 shows the total yield and dollar value in 1974 for the five major
species of. commercial finfish in the New York Bight. Although the stock of
most commercial species is still substantial, there has been a general
decline in annual yields of finfish over the last two decades (Figure 3-5),
with commercial landings of over-fished species (e.g., menhaden) declining.
The yield of the domestic shellfishery has greatly increased since 196U
(Figure 3-6) with the developing surf clam fishery. While surf clams are
becoming increasingly scarce, other shellfish species have only recently begun
to be exploited (e.g., red crab), and potential resources still exist, such as
ocean quahog. Table 3-2 shows the total annual values in 1974 and 1976 for
the more important shellfish species. The American lobster is the most
important species fished in the Continental Slope area, and is becoming the
most important fishery resource of the New York Bight (Chenoweth, 1976).
FOREIGN FISHERIES
Nearly all foreign fishing in the north and mid-Atlantic region of the
United States is in the Continental Shelf area, vessels being mainly
concentrated in the outer Shelf region south of Georges BanK (Figure 3-7).
Peak foreign fishing activity in the New York Bight occurs during spring and
early summer when the fleet moves south from the winter fishing grounds on tne
Georges Bank. An average of 1,000 foreign vessels fish along the mid-Atlantic
coast annually (Ginter, 1978). Foreign fishing in the New York Bight is
dominated by the Soviet Union, followed by East Germany, Spain, and Japan.
Major foreign fisheries are herring, silver and red hake, and mackerel. The
seasonal migrations of these species account for the north-to-south movement
of the foreign fleet throughout the year. Recently, fishing efforts have also
been directed towards squid, butter fish, tuna, and saury.
3-14
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TABLE 3-1. TOTAL LANDINGS IN 1974 OF FIVE MAJOR COMMERCIAL FINFISHES
IN THE NEW YORK BIGHT
Species
Fluke
Menhaden
Scup
Striped
Bass
Whiting
New York
UOO lb
2,487
57b
3,635
1,409
1,955
$000
846
18
832
533
250
New Jersey
000 lb
3,499
107,307
6,040
714
7,022
$000
1,153
2,735
880
177
587
Total
000 lb
5,986
107,883
9,675
2,123
8,977
$000
1,999
2,753
1,712
710
837
Source: Adapted from NOAA-NMFS, 1977
Table 3-2. TOTAL COMMERCIAL LANDINGS IN 1974 AND 1976 OF IMPORTANT
SHELLFISH SPECIES IN THE NEW YORK BIGHT (NEW YORK-NEW JERSEY)
Species
American Lobster
Hard Clams
Surf Clams
Oysters
Sea Scallops
Blue Crabs
1974
000 Lb
1,922
9,769
26,608
2,563
1,228
2,864
$000
3,312
15,164
3,667
4,778
1,689
725
1976
000 Lb
1,117
10,072
9,493
2,256
1,953
407
$000
2,368
19,396
3,299
5,642
3,170
123
Source: From NOAA-NMFS, 1977a, 1977b
3-15
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35
30
| 25
O
H 20
O
I/)
Q
I '5
V)
O
I 10
1880 1890 1900 1910 1920 1930 1940 1950 1960 1970
Figure 3-5. Total Landings of Commercial Marine Food Finfishes
in the New York Bight Area, 1880-1975
(From McHugh and Ginter, 1978)
30
25
-------
73°
72°
1. NEW YORK BIGHT ACID SITE
2. NORTHERN AREA
3. SOUTHERN AREA
4. 106-MILE SITE
38= -
72 =
Figure 3-7.
Location of Foreign Fishing off the East Coast of the U.S.
(Adapted from McHugh and Ginter, 1978)
3-17
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RECREATIONAL FISHERIES
The majority of recreational fishing in the New York Bight is confined to
the inner Shelf Waters, which is most accessible to the public, and more sport
species are found there than in the outer Bight (Chenoweth, 1976). The
important species are striped bass, weakfish, bluefish, and mackerel.
Recreational species fished further offshore are bluefin tuna, marlin, and
swordfish. The sport catch often equals or surpasses the commercial landings
of certain species (e.g., striped bass) and significantly contributes to the
economics of several coastal areas. In 1970, 1.7 million anglers caught
1.3 million kilograms (2.1 million pounds) of fish from the North Atlantic
coast.
SAND AND GRAVEL MINING
Sanko (1975) states that "sand Deposits in the Lower Bay of New York Harbor
have been the largest single source of commercial sand for the New York City
metropolitan area since 1963." Although this is the only area in the New York
Bight where sand is presently mined, recent geological surveys show that sand
could be mined nearly anywhere in the New York Bight, with current technology
limiting the outer boundary to the 50 m (165 ft) isobath.
2 2
There is an estimated area of over 2,680 km (777.2 nini ) suitable for sand
mining between the 50 m isobath and the Long Island shoreline (Schlee, 1975).
Most of this sand is of uniform grain-size and contains a low percentage of
fine particles. Gravel deposits in the New York Bight are much more limited
than sand. Potential mining areas for gravel are few, mainly off the northern
coast of New Jersey (Figure 3-8).
OIL AND GAS DEVELOPMENT
No existing or planned oil and gas lease tracts are located in any interim
or designated ocean disposal site. Figure 3-9 is an EPA (1978a) summary of
oil and gas development in the New York Bight.
3-18
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75°
74°
73°
72°
41
1 NEW YORK BIGHT ACID
WASTE DISPOSAL SITE
2. NORTHERN AREA
3. SOUTHERN AREA
4. 106-MILE CHEMICAL
WASTE DISPOSAL SITE
40;
39
38:
41°
40°
39°
KILOMETERS
0 50
NAUTICAL MILES
100
50
38'
74=
73°
72°
Figure 3-8. Gravel Distribution in the New York Bight (Schlee, 1975)
J-19
-------
1. NEW YORK BIGHT ACID SITE
2. NORTHERN AREA
3. SOUTHERN AREA
4. 106-MILE SITE
38° -
Figure 3-9. Oil and Gas Leases in the mid-Atlantic Bight
(Adapted from EPA, 1978a)
3-20
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The U.S. Department of the Interior's Bureau of Land Management (BLh)
completed its first sale of oil and gas leases in the mid-Atlantic Baltimore
Canyon trough in August 1976 (Outer Continental Shelf [OCSJ Sale Wo. 40).
Exploratory drilling at o of the 93 tracts leased in DCS Sale No. 4u oegan in
the spring ana summer of 1978. On May 19, 1978, BLM published a draft EIS on
the OCS Sale No. 49, including most of the Baltimore Canyon trough, bale No.
49 was neld in May 1979. A third sale (No. 59) is under consideration and is
tentatively scheduled for August 1981 (JbLM, 1978).
SHIPPING
Ine major trade routes identified by NOAA, (TRIGOi>i, 1976) to serve the new
York-New Jersey area coincide with the three traffic lanes into New YorK
Harbor: tne Nantucket, Hudson Canyon and Barnegat Traffic Lanes (Figure
3-10). Barnegat Lane lies across the Acid Site, and the other lanes straddle
tne Northern and Southern Areas.
OCEAN WASTE DISPOSAL
The EPA (1979) permits municipal or industrial waste disposal at six
locations in the New York Bight, and the CE permits dredged material disposal
at otner sites (Figure 3-11). This section briefly describes activities at
tne six sites, but not the Acid Site (Figure 3-11, f/4) .
SEWAGE SLUDGE SITE
Sewage sludge is composed of residual municipal sewage solids from primary
ana secondary treatment plants. The present sewage sludge site was
established in 1924 (Figure 3-11, #5). There are 25 permittees currently
(1979) disposing of sewage sludge at this site, witn the City of New Yortc
discharging more than any other permittee. The total volume of sewage sludge
3
to be discharged in 1979 is estimated to be 7,770 m and is predicted to be
9,890 m3 in 1981.
3-21
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75
1. NEW YORK BIGHT ACID SITE
2. NORTHERN AREA
3. SOUTHERN AREA
4. 106-MILE SITE
39° -
38° -
- 38°
Figure 3-10. Traffic Lanes in the mid-Atlantic Area
3-22
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LONG ISLAND SOUND
KX- •' LONG ISLAND
1. DREDGED MATERIAL
2. CELLAR DIRT
3. SEWAGE SLUDGE
4. ACID WASTES
5. SEWAGE SLUDGE (ALTERNATE)
6. WRECKS
7. WOOD INCINERATION
NEW YORK
BIGHT LIMIT
DELAWARE
BAY
50
NAUTICAL MILES
73°
72°
Figure 3-11. Ocean Disposal Sites in the New York Bight
-------
The alternate sewage sludge site (Figure 3-11, #5) was designated in 1979
for use if the existing site cannot handle the increased volumes of sludge
before ocean disposal ends in 1981. No sludge has yet been released at this
site.
DREDGED MATERIAL SITE
Several sites have been used for the disposal of material dredged from
navigable waterways in the New York-New Jersey Metropolitan area. Use of the
present site (Figure 3-11, #1) began in 1940. Until 1973, fly ash residues
from fossil-fueled power plants were released at the site.
Each year, the volume of dredged material exceeds that of any other waste.
The average annual volume of dredged material for the period 1960 to 1977 was
approximately 6 million m . The annual volume is estimated to increase by
another 46,000 to 54,000 m . Some dredged material is contaminated because
particulate solids carried in the Hudson River settle in the harbor.
Other dredged material sites exist just outside the inlets along the Long
Island and New Jersey shoreline (not shown in Figure 3-11). Much lower
volumes of sediment are released at these sites and this material is
relatively uncontaminated sand.
CELLAR DIRT SITE
The Cellar Dirt Site (Figure 3-11, #2) has been relocated several times to
prevent excessive moundings of the waste. The site has occupied its present
location since 1940. Inert materials from land-based construction projects
(demolition wastes), including excavated earth, broken concrete, rock, and
other nonfloatable materials, are dumped at the site. The average annual
•j
volume of cellar dirt released at the site from 1960 to 1977 was 450,000 m .
The annual volume will fluctuate from year to year according to the activity
of the construction industry and the availability of alternate disposal
methods.
3-24
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WRECK SITE
The Wreck Site (Figure 3-11, #6) has been designated by the EPA for
derelict and wrecked vessels. The site has been used infrequently since 1962,
and in 1977 was moved slightly to avoid interference with shipping.
WOOD INCINERATION SITE
The EPA has designated the Wood Incineration Site (Figure 3-11, if!) for
burning and disposal of scrap wood from harbor debris, pier pilings, and
waterfront construction sites. The site is used as needed ana only the
combustion products reach the ocean. The remaining ash is buried in sanitary
landfills.
MARINE RECREATION
The shorelines of Long Island and northern New Jersey support an estimated
$2-billion per year beach industry (Interstate Electronics Corporation, 1973).
The popularity of the low, sandy beaches is due to their quality and access-
ibility. Beach property in the New York-New Jersey metropolitan area is both
publicly and privately owned. In the metropolitan area, the 1976 beach
attendance, at state and national parks alone, was over 20 million
(Table 3-3).
ALTERNATIVE SITE OFF THE CONTINENTAL SHELF - 106 MILE CHEMICAL WASTE SITE
SITE ENVIRONMENT
The 106-Mile Chemical Waste Disposal Site (.Figure 3-12; is in an area
typical of the Atlantic Continental Slope and upper Continental Rise. The
physical and chemical characteristics of the site are highly complex, with
great, natural variability. The sediments and benthic biota are typical of
deep-water, silt-sand sediments. Although disposal of chemical wastes began
at the site in 1961, measurable changes caused by the wastes have not
occurred.
3-25
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TABLE 3-3. BEACH ATTENDANCE AT STATE AND NATIONAL irARKS IN THE
NEW YORK-NEW JERSEY METROPOLITAN AREA 1976
Park
Attendance
Island Beach State Park, N.J.*
Gateway National Recreation Area
Breezy Point, N.Y. (Jacob Riis State Park)+
Sandy Hook, N.J.+
Staten Island, N.Y.+
Smith Point Co. Park, Fire Island, N.Y.**
Robert Moses State Park, Fire Island, N.Y.**
Captree State Park, Long Island, N.Y.++
Fire Island National Seashore, N.Y.**
Fire Island "Other," N.Y.***
Jones Beach State Park, N.Y.++
Total
194,223
3,800,000
2,OUO,UUU
1,240,000
735,256
2,122,200
500,000
702,194
2,301,000
7,000,000
20,594,873
Sources:
* New Jersey Department of Environmental Protection, Bureau of Parks, 1978.
+ National Park Service, May 1978.
** Fire Island National Seashore Headquarters, 1978.
++ Long Island State Parks and Recreation Commission Headquarters, June 1978.
*** National Park Service, 1975.
PHYSICAL CONDITIONS
The site is located within the influence of the Gulf Stream and three
different water masses (Shelf Water, Slope Water, Gulf Stream hater), each
having distinctive physical, chemical, and biological characteristics, which
may be present in the site.
Slope Water normally occupies the site; however, when the Shelf/Slope ocean
front migrates eastward, Shelf Water of equal or lower salinity and
temperature mixes with Slope Water. The differing densities of the water
masses causes formation of separate layers. Therefore, the mixing of waters
at the site can be quite complex, influenced by highly unpredictable factors
and normal seasonal changes (Warsh, 1975).
Occasionally, warm-core rings of water (called eddies) break off from the
Gulf Stream and migrate through the site, entraining Gulf Stream water or wari
Sargasso Sea water. Both are of higher temperature and salinity than Slope
3-26
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72°
70rW
0 100
NAUTICAL MILES
HUDSON
CANYON
38°N
Figure 3-12. Location of the 106-Mile Site
Water. Eddies do not pass through the site on a seasonal basis; they occupy
part or all of the site about 70 days a year (Bisagni, 1976).
As the surface waters of the site warm in late spring, they stratify within
the top 10 to 50 m forming layers of water with differing temperatures,
salinities, and densities. This stratification (thermocline), which can occur
within one water mass without any mixing witn another water mass, persists
until September/October, when cooling and storm activity destroy it. From
autumn to early spring, the temperature of the water column is the same from
the surface to a depth of approximately 200 m. At 200-m depth, however, a
3-27
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permanent stratification exists. Deeper water always has a lower temperature.
These characteristics are important because they greatly influence the
ultimate fate of liquid waste discharges.
Although few ocean-current measurements (1979) exist for the &ite, the
literature indicates that water at all depths in this area tenas to flow
southwest, generally following the boundary of the Continental Shelf and
Continental Slope (Warsh, 1975). Changes in the direction of flow are usually
associated with Gulf Stream eddies. The flow direction may change even in
deep water. Water motion is important because it provides information as to
the directions waste discharges may follow.
The physical and chemical characteristics of the site cause biological
complexity because each water mass possesses characteristic associations ot
plants and animals.
GEOLOGICAL CONDITIONS
The Continental Slope witnin the disposal area has a gentle (4 percent)
grade, leveling off (1 percent) outside the site, in the region of the upper
Continental Rise. Sediments within the site are principally sand and silt,
with silts predominating (.Pearce et al., 1975). The sediment composition is
an important factor which determines the types of animals found in an area.
Generally, greater diversity and abundance of fauna is associated with finer
sediments (e.g., silt), although unusual physical conditions will alter this.
Fine-grained sediments commonly have higher concentrations of heavy metals.
Sand, gravel, and rocky bottoms rarely contain such elements in high
concentrations.
Continental Slope sediments across the site are subject to different
dynamic forces; the upper Continental Rise is an area of tranquil deposition,
and the lower Continental Rise is an area of shifting deposition. Erosional
areas (caused by bottom currents) lie between these two provinces. These
different processes would largely determine the ultimate fate of any waste
products (probably insignificant) whicn reach bottom. In areas swept by
currents, waste products would be carried out of the disposal site, greatly
3-28
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diluted before being buried. In erosional and shifting depositional areas,
the waste material may be temporarily deposited before being moved. In areas
of tranquil or slow deposition, waste products would be slowly buried.
CHEMICAL CONDITIONS
Dissolved oxygen concentrations at the 106-Mile Site follow the temperature
gradients; the permanent stratification level at 200 m divides the water into
upper and lower regimes. The different water densities of these regimes (due
to differences in temperatures and salinities) keep the two layers distinc-
tively different, and no mixing occurs. Dissolved oxygen levels decline from
surface levels to a natural minimum between 200 to 300 m, then slowly increase
with depth. Figure 3-13 illustrates that summer and winter dissolved oxygen
gradients are similar, with slightly higher surface concentrations during
winter. Acid wastes, which have not caused oxygen depletion problems in the
Apex, would not significantly change these natural conditions.
Chemical surveys and monitoring programs at the 106-Mile Site have studied
trace metal levels in sediments, water, and selected organisms. Metals in the
sediments and water represent contaminants potentially available to site
fauna, and may possibly be assimilated (bioaccumulated) and concentrated by
them in toxic quantities.
Since metals are naturally present in seawater, only concentrations of
metals which exceed natural background levels and approach known or suspected
toxic levels threaten the marine fauna or man. The most recent studies of
trace metal currents in the water of the 106-Mile Site found near-background
levels typical of other Shelf-Slope regions (Kester et al. , 1977; Hausknecht
and Kester, 1976a, 1976b).
Trace metals in sediments all along the Continental Slope and Rise
(including the site area) are elevated in comparison to Continental Shelf
values (Greig et al. , 1976; Pearce et al. , 1975). However, these values are
widespread, thus they cannot be attributed to waste disposal activities at the
site.
3-29
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OXYGEN (mg/1)
4 5 6 7
" 'A
8
OXYGEN(mg/l)
456
£300
400
500:
600
700
800
900
1000i
2000;
3000
- FEB - MAY
1 1 I
- AUG-DEC \l\
Figure 3-13. Monthly Averages of Oxygen Concentration Versus Depth
at the 106-Mile Site (from Warsh, 1975)
Analyses of trace metal concentrations in finfish caught at the site
revealed high cadmium levels in three swordfish livers, mercury levels above
the Food and Drug Administration action level ("unfit for human consumption11)
in most fish muscle samples, and low to moderate copper ana manganese
concentrations, similar to those in New York Bight finfisn (Greig and
Wenzloff, 1977; Greig et al., 1976). However, since the fish were migratory
and transient species, and the levels in benthic organisms were similar over a
large area, waste disposal was not suggested as the "cause" of the elevated
metal concentrations; other factors were important (Pearce et ai., 1975).
3-30
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BIOLOGICAL CONDITIONS
Plankton are microscopic plants and animals which drift passively with the
current or swim weakly. Plankton are divided into plants (phytoplankton) and
animals (zooplankton). Since the plankton are the primary source of all food
in the ocean, their health and ability to reproduce is of crucial importance
to all life in the ocean, including fish and shellfish of commercial
importance.
Plankton populations at the 106-Mile Site are highly diverse due to the
influence of the Shelf, Slope, and Gulf Stream Water masses. Diatoms dominate
in Shelf Waters while coccolithophorids, diatoms, dinoflagellates, and other
mixed flagellates are important in the low-nutrient Slope Waters (Hulburt and
Jones, 1977). Mixed assemblages of zooplankters (common to the different
water masses) occupy the site during winter, spring, and summer (Sherman et
al., 1977; Austin, 1975).
Fish have been surveyed at various depths within the site. The diversity
and abundance of near surface fish is similar inside and outside the disposal
site (Haedrich, 1977). Fish occurring primarily at mid-depths (mesopelagic
fish), are dominated by Slope Water species with anticyclonic (clockwise)
eddies bringing in some north Sargasso Sea species (Kreuger et al., 1975,
1977; Haedrich, 1977). For some depths, particularly in the lower water
column, the density of mesopelagic fish may be lower at the site when compared
with nondisposal site areas (Krueger et al., 1977). Several migratory oceanic
fish, usually associated with the Gulf Stream, are found in midwater regions
of the site. The diversity and abundance of benthic (bottom) fish in the site
area are similar to those in other Slope areas (Musick, et al., 1975; Cohen
and Pawson, 1977). Fifty-five species have been reported at the site.
Numbers of individuals and numbers of species decrease with depth.
At the bottom, the abundance and diversity of invertebrates at the ll)6-Mile
Site are similar to other Slope localities of the mid-Atlantic Bight.
Invertebrates living on the surface of the bottom (the epifauna) of the
106-Mile Site are dominated by echinoderms (such as starfish and sea urchins),
while segmented worms (polychaetes) are the dominant burrowing organisms.
3-31
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WASTE DISPOSAL AT THE SITE
PERMITS AND WASTE VOLUMES—1973 to 1978
The 106-Mile Chemical Waste Site was proposed for use in 1965 by the U.S.
Fish and Wildlife Service as an alternate to inland discharge of industrial/
chemical wastes which might contaminate potable water supplies. However,
chemical wastes were released in the area during 1961, 1962, and 1963. From
1961 to 1978, approximately 4.6 million tonnes of chemical wastes and
400,000 tonnes of sewage sludge were released at this site, an average of
275,300 tonnes per year.
When ocean waste disposal came under EPA regulation in 1973, there were 66
permittees at the site. Since then, the number of permittees has steadily
declined until, as of November 1979, only four permittees remain: American
Cyanamid (.Linden, N.J.), E.I. du Pont de Nemours and Co., Inc. Edge Moor Plant
(Edge Moor, Del.) and Grasselli Plant (Linden, N.J.), and Merck & Co. (Rahway,
N.J.). The volume of waste released, however, increased from 299,000 tonnes
in 1973 to 735,000 tonnes in 1977. The increase was due to four factors:
(1) the relocation of industrial waste generators from the Sewage Sludge Site
in 1974, (2) Du Pont-Gr asselli' s move from the Acid Site in 1975,
(3) Du Pont-Edge Moor's move from the Delaware Bay Acid Site in 1977, and (4)
the relocating by court order, of waste disposal operations of the City of
Camden, New Jersey to the site in 1977. Camden, however, contributed only
48,000 tonnes. In 1978, the volume of waste dumped totalled 612,000 tonnes,
representing a 16% decrease from the higher volume in 1977. Overall,
approximately 80% of the waste discharged from 1973 to 1978 was from three
industrial sources: Du Pont-Edge Moor, Du Pont-Grasselli, and American
Cyanamid. The actual dumping volumes of each permittee appear in Table 3-4.
Table 3-5 shows the projected inputs to the site from 1979 to 1981.
3-32
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TABLE 3-4. WASTE VOLUMES, 1973 - 1978 AT 106-MILE CHEMICAL WASTE SITE
IN THOUSANDS OF TONNES
Permittee
American Cyanamid Co.
Camden, N.J.
Chevron Oil Co.
Du Font-Edge Moor
Du Pont-Grasselli
Hess Oil Co.
•it
Mixed Industries
**
Mixed municipalities
Totals
1973
118
—
25
—
116
7
34
41
341
1974
137
—
26
—
155
—
35
93
446
1975
116
—
22
—
264
—
78
96
576
1976
119
—
—
—
164
—
67
25
375
1977
130
48
—
380
107
—
85
16
766
1978
111
54
—
372
172
—
72
16
797
Totals
731
102
73
752
978
7
371
287
3,301
Average
122
51
24
376
163
7
62
48
* Crompton and Knowles, Merck and Co., and Reheis Chemical Co.
** Permittees using New York Bight Sewage Sludge Site (sewage sludge digester cleanout residue).
Source: Data from EPA Region-II permit files
-------
TABLE 3-5. PROJECTED VOLUMES, 1979 - 1980, AT 106-MILE CHEMICAL WASTE SITE
(THOUSANDS OF TONNES)
Permittee
American Cyanamid
Du Font-Edge Moor
Du Pont-Grasselli
Merck
Annual totals:
Scheduled Phaseout Date
April 1981
May 1980
None
April 1981
Year
1979
123
299
295
36
753
I960
123
136
295
36
590
1961
30
0
295
10
335
WASTE TYPES AND CONTAMINANTS
The types of wastes, physical characteristics, authorized discharge rate,
and dispersion factors are summarized in Table 3-6. The averages and ranges
of concentrations of selected trace metals are presented in Table 3-7. Table
3-6 shows that the different wastes have some common characteristics. The
wastes are heavier than seawater, although American Cyanamid wastes are almost
neutrally buoyant. Minimal dilution after initial mixing ranges from 20,000
to 25,000:1 up to 75,000:1. The authorized discharge rates have been
established by EPA-Region II to prevent long-term adverse effects caused by
the waste discharges. Comparing the mean and maximal trace metal concen-
tration (Table 3-7) with the minimal dilution factors (Table 3-6) shows that,
with few exceptions, even maximal concentrations of waste constituents are
diluted well below predischarge ambient levels within 4 hours after a waste
disposal operation.
TOXIC1TY
Periodic toxicity bioassays are required of each permittee at the 106-iMile
Site. Table 3-3 summarizes the results for the remaining waste generators.
These results show the variability common to tests of this type and probable
variability in the toxicity of different bargeloads of waste. The EPA
established the discharge rates (Table 3-6) based upon tne more conservative
bioassay results.
3-34
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TABLE 3-6. PHYSICAL CHARACTERISTICS FOR THE WASTES AT THE
106-MILE CHEMICAL WASTE SITE
Company
American Cyanamid
Du Font-Edge Moor
Du Pont-Grasselli
Merck & Company
Waste Produced
From the Manufacture of:
Rubber, mining and paper
chemicals, nonpersistent
organophosphorus pesticides
and surfactants
Titanium dioxide (chloride
process) iron chloride and
hydrochloric acid
DMHA and Anisole
Thiabendazole
( Pharmaceuticals)
N umb e r of
Barge Trips
Per Month
7
7
7-9
1-2
Mean Specific
Gravity (Range)*
1.02S
(1.010-1.055)
1.135
(1.085-1.218)
1.109
(1.036-1.222)
1.115
(1.022-1.132
pH
(Range)**
2.7 to
8.3
0.1 to
1.0
12.4 to
13.6
5.2 to
10.3
Authorized Discharge
Rate
(per nautical mile)
113,400 liters
(30,000 gallons)
140,000 liters
(37,000 gallons)
197,000 liters
(52,000 gallons;
492,000 liters
130,000 gallons)
Minimum Dilution and
Dispersion 4 Hours
After Waste Release
25,000:1
75,000:1
30,000:1 to
55,000:1
20,000:1 to
52,000:1
I
u>
Sources: Data from EPA-Region II permit files
* Specific Gravity of seawater = 1.025
** pH of seawater = 7.8 to 8.4
-------
TABLE 3-7. AVERAGE METAL CONCENTRATIONS (in ug/1) FOR THE WASTES
AT THE 106-MILE CHEMICAL WASTE SITE
Metal
Arsenic
Cadmium
Chromium
Copper
Lead
Mercury
Nickel
Zinc
Seawater
Concentration
2-3
0.15
1
3.0
0.03
0.05-0.19
5-7
10
Reference
Kopp, 1969
Fleischer et al . , 1974
EPA, 1976
Mero, 1964
Home, 1969
Robertson et al. , 1972
NAS, 1974
EVA, 1976
American Cyanamid
Mean
620
4
550
350
120
30
1,100
560
Range
20-2,600
1-150
45-4,900
1-4,100
1-1,000
1-200
145-6,400
7-5,150
Du font-Edge Moor
Mean
140
320
270,200
3,250
40,540
30
29,060
100,960
Range
5-525
20-900
52,600-900,000
4-7,400
2,700-76,000
1-500
200-65,000
110-530,000
Du Pont-Grasselli
Mean
7
170
330
3,150
900
7
730
540
Range
1-30
3-7UO
10-3,500
25-154,700
10-4,900
1-20
30-2,000
30-2,700
Mixed Industries
Mean
30
3,200
21,170
10,900
8,840
300
4,900
163,800
Range
1-130
20-15,600
4-170,000
1-115,000
8-62,000
21-3,830
20-31,500
15-1,400,000
o-
I
Source: Data from EPA Region-II permit files
-------
TABLE 3-8. TOXICITY BIOASSAYS FOR WASTES AT THE 106-MILE CHEMICAL WASTE SITE
Company
American
Cyanamid
Du Font-
Edge Moor
Du Pont-
Grasselli
Mixed
Industries
( includes
wastes other
than Merck)
Menidia
(Minnow
Aerated
0.24 to
2,900
5,000
1.8 to
6,950
650 to
100,000
menidia
96-h TL5Q)
Unaerated
0.10 to
2,900
5,000 to
14,400
1.7 to
6,170
150 to
100,000
Skeletonema costatum
(Phy to plankton-diatom)
96-h EC5Q
10 to 1900
712 to 3,450
29 to 8,600
65 to 12,000
Acartia tonsa
(Zooplankton-copepod)
96-h TL5Q
19.5 to 3,500
No data
57 to 238
29.7 to 5,300
Source: Data from EPA - Region II permit files
-------
In addition to these bioassays, the Du Pont plants have sponsored additional
laboratory work on the toxicity of their wastes. For wastes from the Edge
Moor Plant, Falk and Phillips (1977) concluded that:
• In 200-day chronic toxicity tests, the "no-effect" level for
Mysidopsis j>ahia (opossum shrimp) and Cyprinidon variegatus
(sheepshead minnow) ranged from 25 to 50 ppm.
• pH-neutralizeci waste (which rapidly occurs in seawater) produces
mortalities only at concentrations several orders of magnitude above
the unaltered waste.
• Pulsed exposure of Palaemonetes pugio (grass shrimp) to initial
wastewater concentrations of 250 ppm (v/v)* followed by dilution
slower than that observed in the barge wake produced no mortalities.
0 Maximum waste concentrations in the barge wake were calculated to be
approximately 150 ppm within 2 hours, and about 5 ppm within 8
hours. The 2-hour calculated wake concentrations is about half the
acute LC5a value range of 240 to 320 ppm and the 8-hour wake
concentration is a fifth of the calculated chronic no-effect level
of 25 to 50 ppm for unaltered waste.
Based on these results, Falk and Phillips (.1977) concluded that the Edge
Moor wastewaters can be discharged into the marine environment over a 5-hour
period, at a barge speed of 6 kn, without adverse impact and without violating
the requirements of Section 227.8 of the EPA Ocean Dumping Regulations.
For wastes from the Grasselli plant, Falk and Gibson (1977) concluded:
• Under oceanographic conditions least likely to enhance dispersions
peak wastewater concentration in the barge wake is about 450 ppm
(v/v) 1 minute after release.
• Wastewater concentrations decline to a maximum of 80 ppm 4 hours
after release, and to about 60 ppm after 12 hours.
• In 178-day chronic toxicity tests, the no-effect level for
Mysidopsis bahia (opossum shrimp) and Cyprinodon variegatus (sheeps-
head minnow) was 750 ppm.
• The wastewaters are not selectively toxic to a particular life stage
°f Cyprinodon or Mysidopsis.
• There is little difference in the toxicity of the wastewater to
several species of marine organisms.
* v/v - volumetric ratio
3-38
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These results supported the discharge of Grasselli waste into the site over
a 5-hour period, at a barge speed of 5 kn without adverse impact, and without
violating the requirements of Section 227.3 of the EPA Ocean Dumping
Regulations.
CONCURRENT AND FUTURE STUDIES
The NOAA Ocean Dumping Monitoring Division will continue monitoring tne
106-Mile Site to detect any long term changes due to the chemical wastes
released. All permittees are required to monitor the short-term effects of
their waste discharges. Present permittees have contracted with a private
company to conduct continuous monitoring, and twelve reports (as of 1979J have
been submitted to EPA-Region II.
OTHER ACTIVITIES IN THE 106-MILE SITE VICINITY
Few activities occur in the site vicinity other than waste Disposal
operations at the site itself. A large area immediately south of the site has
been proposed as an ocean incineration area; however, there are no otner
active ocean disposal sites in the vicinity. Oil ana gas lease tracts are
located west and north of the site, along the outer Continental Shelf (Figure
3-9). While the Hudson Canyon Navigational Lane crosses the Continental Slope
to the north of the site, major traffic lanes are not near the 106-Mile Site.
Limited fisheries resources occur at the 106-Mile Site and vicinity. Due
to the abyssal depths at the site, none of the shellfish common to shallower
Shelf-Slope areas are found at the site. Lobsters, which are a valuable
fisheries resource in the New York Bight, are confined to areas shallower than
50U m. The red crab (a potential fishery resource) is most abunaant at cieptns
between 310 and 914 m; its depth range is to 1,S30 m. Small individuals may
occur at the site; however, liquid wastes would not affect bottom dwelling
animals.
Existing population data show that commercially important species of
finfishes in the New York Bight vicinity are most abundant in Shelf areas and
along the Continental Shelf-Slope break (MESA, 1975; BLM, 1978; Chenowetn et
3-39
-------
al., 1976). Consequently, most foreign and domestic fish trawling is conducted
at depths shallower than 1,000 m, much shallower than the lOG-Mile Site.
Nearby waters have been used for the commercial longline fishing of marlin,
swordfish, and tuna (Casey and Hoenig, 1977). However, only 1,041 of these
fisii were taken in 1973 and 1974 in a large area including the 106-Mile Site.
In general, catch statistics for Continental Slope areas are unavailable
because landing records do not separate Shelf species from Slope species.
ALTERNATIVE SITES ON THE CONTINENTAL SHELF
In addition to existing disposal sites, the so called Northern and Southern
Areas were evaluated as alternative sites for the release of acid wastes.
These sites might be considered if disposal operations were moved out of the
New York bight Apex, but not off the Continental Shelf due to environmental or
economic considerations. The Alternate Sewage Sludge Disposal Site is in the
rortheast corner of the Northern Area, but antnropogenic wastes have never
been released in either location.
The main environmental features of the two areas are similar to those
discussed earlier in this chapter for the Acid Site, and detailed in
Appendix A. This section empnasizes the most significant differences between
the areas, and the general oceanography of the New York Bight. The
information is taken from NOAA (1976).
The flow of waters is generally southwestward, following depth contours,
although (as in the Apex) this flow is highly variable and subject to intense
meteorological events. Flow in the Hudson Canyon is both up and down the
canyon, but the long-term flow is distinctly up-canyon, towaras the Bight
Apex.
Surface sediments are mostly clean, medium-sized sands. The most prominent
feature of the bottom sediment in the Southern Area is a band of coarse,
gravelly sand near the northeast rim of the site, parallel to the Hudson Shelf
Valley. The motion in both areas is generally towards the southwest,
especially during winter "northeaster" storms.
3-40
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Dissolved oxygen concentrations in surface, mid-depth, and bottom waters in
the Northern and Southern Areas are moderately to highly saturated under
winter, spring, and critical summer conditions. The saturation value for
oxygen at these sampling depths probably does not fail below 50^ at any time
of year, and is usually much higher (75£ to 110%).
The concentrations of heavy metals in the sediments and waters of the
Northern and Southern Areas are low compared to those found in the Bight Apex,
but all levels of chemical parameters are typical of the New York liignt.
Concentrations of suspended particulate matter are lower in these areas since
they are further removed from shore influence.
The living marine resources are typical of those along the mid-Atlantic and
New England Continental Shelf. NOAA (1976) reported surf clams and sea
scallops at each site. Commercial possibilities were not determined. Ocean
quahogs were also present in both areas. Figure 3-2 shows tne distribution of
these three species.
3-41
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er 4
ENVIRONMENTAL CONSEQUENCES
The release of acid waste at any of the alternative sites
would produce similar environmental consequences. There will
be minor, short-term, adverse effects on the plankton and
minimal effects on bottom-living organisms. Effects on the
benthos are most probable and would be easiest to demonstrate
at the Southern or Northern Areas; effects (if present) at
the Acid Site are obscured by the multiple contaminant
sources, while no effects are expected at the 106-Mile Site,
which is located in water depths of 2,000 m.
Adverse effects from acid waste disposal on the public health
and water quality will be minimal except for a site in the
Southern Area,, where acid waste disposal might interfere with
development of exploitable shellfish resources. Demon-
strable, adverse effects on the ecosystem are most probable
at a new site in the Northern or Southern Areas since wastes
have never been released in these regions.
Most importantly, 30 years of study at the existing New York
Bight Acid Waste Disposal Site have not demonstrated any
adverse effects resulting from the disposal of these wastes.
There may be a beneficial effect of waste release if
bluefish, a popular sport fish, are attracted to the area by
the discolored water caused by waste discharge. The
alternative sites are too distant from shore to support an
active sportfishery.
This chapter details environmental effects of waste disposal at various
alternative disposal sites outlined in Chapter 2. Included are unavoidable
environmental consequences which would occur if the proposed action takes
place. The effects discussed first are environmental changes which directly
affect public health, specifically, commercial or recreational fisheries and
navigational hazards. Secondly, the environmental consequences of acid waste
disposal at each alternative site, which cover effects of short dumping in
nondesignated areas, are discussed. Finally, the chapter concludes with
descriptions of unavoidable adverse effects and mitigating measures, the
relationships between short-term uses of the environment, maintenance and
enhancement of long-term productivity, and any irreversible or irretrievable
commitments of resources which would occur if the proposed action is
implemented.
4-1
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Much data and other information was examined to evaluate potential effects
of acid waste disposal at the sites. The principal data sources for each area
are:
0 New York Bight Acid Waste Disposal Site: NOAA-MESA studies
beginning in 1973. NMFS/Sandy Hook Laboratory study from 1968 to
1972. Site-specific studies sponsored by NL Industries, Inc.,
beginning in 1948. Routine monitoring surveys sponsored by the
permittees.
• 106-Mile Site: NOAA surveys, starting in 1974. Waste dispersion
studies and monitoring of short-term disposal effects sponsored by
the permittees. Public hearings concerning relocation of sewage
sludge disposal sites and issuing of new permits.
• Southern Area: NOAA survey in 1975. Public hearings concerning the
disposal of sewage sludge in the New York Bight.
* Northern Area: NOAA and Raytheon Corporation surveys in 1975.
Hearings concerning the disposal of sewage sludge in the New York
Bight.
Information from these and other sources was collected and compiled into an
extensive data base entitled Oceanographic Data Environmental Evaluation
Program (ODEEP) (Appendix D). The following discussion is based on an
evaluation of the available data.
EFFECTS ON PUBLIC HEALTH AND SAFETY
A primary concern in ocean waste disposal is the possible direct or
indirect link between contaminants in the waste and man. A direct link may
affect man's health and safety. An indirect link may cause changes in the
ecosystem which, although not apparently harmful to man, could lead to a
decrease in the quality of the human environment.
4-2
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COMMERCIAL AND RECREATIONAL FISH AND SHELLFISH
Ttie most direct link between man and waste contaminants released into tne
marine environment is via consumption of contaminated seafood. Snellfishing,
for example, is automatically prohibited by the FDA around sewage slucige
disposal sites or other areas wnere wastes are dumped which may contain
disease-producing (pathogenic) microorganisms. Thus, the possibility of
consuming shellfisn which may be contaminated by pathogens, is eliminated or
minimized. Harmful effects caused by eating fish containing high levels of
mercury, lead, or persistent organohalogen pesticides have been documented.
Certain compounds (e.g., oil) have made fish flesh and shellfish unhealthy and
unpalatable. Therefore, wastes containing heavy metals, organohalogens, oil,
or pathogens must be carefully evaluated with respect to possible contami-
nation of commercially or recreationally exploitable marine animals.
Foreign long-line fisheries exist on the Continental blope, but U.S.
fishing in the mid-Atlantic is mostly restricted to waters over the
Continental Snelf. Commercial fishing and sportfishing activities on the
Shelf are widespread and diverse; finfish and shellfish (mollusks and
crustaceans) are taken. The New York Bight is one of the most productive
coastal areas in the North Atlantic, and the region may be capable of even
greater production as new fisheries develop.
Important spawning grounds and nursery areas lie within the Bight, but
critical assessments of the effects of man-induced contamination on fish and
shellfish populations are lacking. Many factors complicate the collection &n
-------
NEW YORK BIGHT ACID WASTE DISPOSAL SITE
There is an extremely low potential for endangering public health from
continued acid waste disposal at this site. The site location was chosen 30
years ago because it was not a point of concentration for fish or fishing and
because the sandy sediments of the site are seldom associated with productive
fishing. Ironically, the site has become a sportfishing area because the
discoloration of the water caused by acid-iron waste disposal apparently
attracts bluefish, a prized sport fish, to the area (Westman, 1953J. However,
fishermen in the New Jersey and Long Island areas claim that the discolored
water hurts the fishing for other pelagic sport fish. In winter a commercial
whiting fishery exists near the Acid Site, and lobstering may occur northeast
of the site.
Effects of acid waste disposal on these resources are practically
nonexistent. The area nearer shore is closed to shellfisning because of the
material released at the Sewage Sludge and Dredged Material Sites.
Acid waste contains only small amounts of tainting substances, such as oil
and grease. Relative to total inputs of oil ana grease to the bight, acia
waste is an insignificant contributor of these contaminants. Waste
constituents may reach the bottom and be assimilated by organisms, but other
sources of contamination are probably more significant. (The New York Bight
Sewage Sludge Site is only 2.8 nmi from the Acid Site.;
No health problems associated with sport fish caught at the site have been
reported. Although adverse effects have been observed in mackerel eggs
exposed to moderately high concentrations of acid waste (Longwell, 1976),
tainting or harmful accumulations of waste components in the flesh of fisti
taken from the area nave not been reported. Long-term damage to the resources
resulting from acid waste disposal have not been documented (EG&G, 1977e;
ERGO, 197cia,b).
1U6-MILE SITE
Commercial or recreational fishing is infrequent at this site; conse-
quently, acid waste disposal will not directly endanger human healtn.
4-4
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Although the NOAA resource assessment surveys do not extend beyond the Shelf,
densities of fish eggs and larvae are low beyond the edge of the Sheif.
Foreign fishermen are near the site in the late winter, but usually catch
tughly migratory fish. The probability of these fish accumulating toxic
levels of contaminants from the waste is extremely unlikely.
A small fishery for the deep sea rea crab (Geryon quinquedens) exists near
the Shelf-Slope break in the mid-Atlantic. Immediately north of the 106-Mile
site, crabs are found in moderate abundance (33 per half nour otter trawl,),
but the water depth is much shallower than at the site Oil to 1 Si ;nj . at a
station 70 nmi (130 km) northeast of the site, at a comparable depth, no crabs
were taken (Wigley et al., 1975). Although the site is within the range of
smaller crabs, none of commercial size were taken deeper tnan 914 m. As with
finfisn, the probability of liquid wastes affecting a benthic animal is
extremely low. Therefore, disposal at this site does not directly endanger
human health by contaminating edible organisms.
SOUTHERN AREA
Although numerous surf clams, ocean quahogs, and scallops are found in the
Southern Area, most commercial shellfishing is presently to the west, near the
New Jersey coast. However, declining harvests may cause the Southern Area to
be exploited in the future (EPA, 1978a). Recreational fishing is unlikely at
this site due to its distance from shore and the competition from more
attractive sportfishing areas closer inshore. If this area were used as a
disposal site for wastes similar to those presently being released at the Acid
Site, a real but low potential for an accumulation of waste constituents in
the flesh of shellfish would exist.
NORTHERN AREA
Disposal of aqueous acid wastes in this area would probably not directly
endanger public health. This site is not in a known commercially or
recreationally important fishing or shellfisning area. Resource assessment
surveys show that this area has a similar, or lower, density of fish eggs and
larvae when compared with other Shelf sites (NOAA, 1975.). Shellfish are not
4-5
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abundant in the area. Since the area supports no commercially or recre-
ationally exploitable finfish or shellfish, a health hazard from eating
animals contaminated by waste materials is unlikely.
NAVIGATIONAL HAZARDS
Navigational hazards may be separated into two components: (1) hazards
resulting from the movement of transport barges to and from a site, and (2)
hazards resulting from barge maneuvers within the site.
If an accident occurred involving the release of wastes, the effects from
the dumped waste would probably be equivalent to a short dump. The effects
from the other ship would depend on the cargo and could be severe if the barge
collided with an oil or liquefied natural gas (LNG) tanker. There is the
possibility of loss of life in any collision. Sites further offshore have a
longer search and rescue response time than sites closer to shore.
For all sites, barges must pass through the Precautionary Zone centered
around Ambrose light, where traffic is densest and hazards are greatest. Once
through the Precautionary Zone, the potential for problems increases with
increasing distance from shore. Table 4-1 shows the distance and estimated
transit time for the four alternate sites.
NEW YORK BIGHT ACID WASTE DISPOSAL SITE
The New York Bight Acid Waste Disposal Site is situated across the outbound
section of the Hudson Canyon Traffic Lane from New York Harbor, but the
barging operations are designed to minimize interference with traffic. In 30
years of use at the Acid Site, no collision between a barge discharging waste
and a ship has ever occurred. In April 1976, a collision did occur near the
Acid Site between a ship and a barge outbound for the 106-Mile Site. The
permittees now using the site barge wastes about once a day. Any accident
would be close to New Jersey or Long Island beaches.
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TABLE 4-1. DISTANCES AND TRANSIT TIMES (ROUND TRIP) TO ALTERNATE SITES
Site
New York
Acid Waste
106-Mile
Chemical
Waste
Southern
Area
Northern
Area
*
Distance
nmi
17
113
53
50
(km;
(31)
(209)
(96)
(93)
**
Transit Time (Hours)
5 kn (9 km/hr)
7
46
22
21
7 kn (13 km/hr)
3
32
16
Ib
* Measured from the Rockaway - Sandy Hook Transect
** Does not include time in transit from the loading dock to tne Rockaway-
Sandy Hook Transect (New York Harbor), nor time spent at the sites.
106-MILE SITE
Barges in transit to the 106-Mile Site from New York Harbor use the
Ambrose-Hudson Canyon Traffic Lane for most of the journey. There is a
slightly greater possibility for problems during the round-trip transit to the
106-Mile Site than to a site closer inshore.
Hazards resulting from maneuvers within the site are negligible. The site
is extremely large, and permittees are required to use different quadrants of
the site if there are simultaneous disposal operations. The frequency of
existing barging is only two to three times per week. Increased frequency of
use would not significantly increase navigational difficulties.
SOUTHERN AREA
The Southern Area lies outside traffic lanes for New York Harbor, thus its
use would cause few navigational hazards. Barges could use the Ambrose-
Barnegat Traffic Lane for most of the trip. However, increased ship traffic
resulting from offshore oil and gas resource development would slightly
-4-7
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increase the hazard. The degree and extent of such hazards would depend on
the speed and magnitude of oil and gas development in the area. Any accidents
would likely occur in the heavily fished coastal waters off New Jersey.
NORTHERN AREA
The Northern Area lies outside traffic lanes for New York Harbor thus its
use would cause few navigational hazards. Barges could use the Ambrose-
Nantucket Traffic Lane for most of the trip. Mineral resources are not
located in the area, so there is no possibility of increased hazards from
future resource development. Any accidents would be near coastal waters off
Long Island.
EFFECTS ON THE ECOSYSTEM
The adverse effects of ocean disposal on the ecosystem (the interacting
living and non-living components of the environment) can be subtle, and may
not exhibit obvious direct effects on the quality of the human environment.
However, subtle adverse impacts can accumulate and combine, to cause long-term
consequences which are as serious as any readily observed direct impacts. For
example, an organism may accumulate waste constituents in its tissues at
concentrations that do not cause its death immediately, but instead act at a
sublethal or chronic level. Sublethal effects may reduce reproduction, reduce
health of eggs and larvae, slow development of juveniles, or affect otner
facets of the life cycles of individual organisms followed by adverse changes
in the entire population of this organism. The population may eventually be
eliminated from an area, not because it was immediately killed by a single
waste discharge but because of long accumulations of sublethal effects. If
that population were a major human food source or a food source for an
organism that was commercially exploited, man could lose the resource. This
scenario is vastly simplified and is not a projection of what is currently
resulting from acid waste disposal in the ocean; however, it does illustrate
that man, as an integral part of a complex ecosystem, may ultimately feel the
results of adverse impacts on other parts of the ecosystem.
4-8
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The magnitude of the effects of waste disposal on the marine ecosystem
depends upon several factors: (1) the types of waste constituents, (2; the
concentrations of toxic waste materials in the water and sediments, (J) the
length of time that high concentrations are maintained in the water or the
sediments, and (4) the length of time that marine organisms are exposed to
high concentrations of these materials. Current disposal techniques for
aqueous chemical wastes maximize the dilution and dispersion of the wastes,
and minimize chances for wastes to remain in the water column or to reach the
bottom in high concentrations.
BIOTA
PLANKTON
Plankton consists of plants (phytoplankton) and animals (zooplankton,) whicn
spend all or part of their lives floating or weakly swimming in the water.
Since aqueous wastes primarily affect the water column, plankton represent the
first level of the ecosystem where the effects of waste disposal could be
observed. Accordingly, numerous studies of the effects of wastes on
planktonic organisms have been conducted.
Acid Waste
Tne effects of waste disposal on plankton at the Acid Site have been
extensively studied, field studies during waste discharges have shown that
acid-iron waste does not harm zooplankton populations (Wiebe et al., 1973;
Redfield and Walford, 1951). Evidence of chromosomal damage in mackerel eggs
collected in the vicinity of the site has been reported (.Longwell, ly?6>, but
the cause of the damage cannot be definitely linked to the disposal of acid
wastes. Interpretation of field results from this site is difficult; changes
in plankton populations resulting from acid waste disposal at the Acid Site
cannot be reliably distinguished from changes caused by pollutants from other
sources introduced into the New York Bight.
Laboratory studies show that acid wastes released at this site can cause
chronic effects in zooplankton after prolonged exposure to waste concen-
4-9
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trations which are much greater than those encountered under field conditions
(Grice et al., 1973). Sublethal effects (e.g., failure to reproduce and
extended developmental times) have been demonstrated in the laboratory after
21 days of exposure to waste concentrations which persist for only minutes
after actual discharge of wastes at the site (Vaccaro et al., 1972).
Additional release of acid wastes at the Acid Site would not be expected to
cause effects different from those presently seen there. However, releasing
wastes with characteristics different from wastes previously dispersed may
have unpredictable effects.
106-Mile Site
Numerous field and laboratory studies on the 106-Mile Site have investi-
gated the effects of dumped wastes on the plankton. Some of these wastes are
aqueous by-product acids, similiar to those at the Acid Site. Field studies
of populations have shown great numerical variations, mainly due to the
presence of several water masses, each with different species (Austin, 1975;
Sherman et al., 1977; Hulburt and Jones, 1977). NOAA (1977) recognized these
factors at the 106-Mile Site:
Plankton undergo large natural variations with changing water
type and for this reason, assessment of the plankton of the
region was difficult. Coastal waters are characterized by
high nutrient concentrations and populations with wide
seasonal variations in abundance and diversity. Oceanic
waters have reduced nutrient levels and population densities,
but photosynthetic processes extend to much greater depths.
Mixing water types will produce a complex combination of
these conditions.
Since plankton data demonstrate high natural variabilities in populations,
changes in species composition, abundance, and distribution data due to waste
disposal may never be demonstrated. Variations induced by waste disposal are
obscured by variability created by natural events.
The adverse effects of acid waste disposal at this site should be localized
and short term.
4-10
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Southern and Northern Areas
Use of either the Southern or Northern Areas for chemical waste disposal
would not be expected to have significant long-terra effects on plankton.
Tnese areas are outside the highly stressed New York Bight Apex, thus their
biota are unlikely to have had the opportunity to adapt to man-induced
environmental stresses. However, specific effects would depend upon the
nature and volume of wastes and frequencies of disposal. Based upon existing
wastes and volumes, any effects would be difficult to demonstrate since
plankton populations are so variable.
NEKTON
The nekton include animals, such as fish and mammals, capable of strong
swimming and migrating considerable distances.
None of the numerous studies on nekton at the New York Bight Acid Waste
Disposal Site have detected long-term effects attributable to acid waste
disposal. Many contaminant inputs to the Bight Apex, other than those at the
Acid Site, make it unlikely that any deterioration of fish health or
populations could ever be proven as caused by acid waste disposal. Therefore,
any effects on fish populations by additional acid waste disposal at this site
are difficult to predict, based on information obtained as a result of the
present disposal operations. However, considering (1) the dilution and
dispersions of wastes presently released, (2) the absence of deaa fish in tne
wake of disposal barges, and (3) the ability of fish to move away from
temporarily stressed areas, it is unlikely that disposal of acid wastes at the
Acid Site would have any demonstrably adverse consequences.
One possible effect under investigation is a relationship between acid
waste disposal and mutagenesis in fish eggs (.Longwell, 1976). Kinne and
Rosenthal (1967) suggested the possibility, while investigating the effects of
sulfuric acid wastes on the larvae of the Atlantic herring (Clupea harengusj;
however, even this effect would be insignificant. No species spawn only in
the vicinity of the site or only in the Bight Apex. Fish eggs and larvae are
4-11
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spread over the entire New York Bight. Concentrations of acid waste are
rapidly diluted to nontoxic levels and would not affect more than a small
number of eggs or larvae.
106-Mile Site
The results of field investigations of effects of chemical waste disposal
on fish at the lUb-Mile Site have been inconclusive. Field work has usually
occurred during the infrequent presence of Gulf Stream eddies, therefore
non-eddy conditions nave not been studied. NOAA (.1977) reported:
Total fish catches within and without the dumpsite were not
significantly different, although midwater fish were most
abundant outside the dumpsite. The highest rate of fishless
tows occurred the night after a dump, but whether the tows
were still in water affected by the dumped material is not
known.
The nistopathology of fish collected from the disposal site area (NOAA
Pathobiology Division, 1978) has been inconclusive. Lesions were observed in
some fish, but the sample size was small. High cadmium levels were found in
the livers of three swordfish from the site area, and high mercury levels were
observed in muscles of almost all fish analyzed (Greig and Wenzloff, 1977).
However, the elevated concentrations were not attributed to disposal
operations at the 106-Mile Site because of the low amounts of these metals
added to the area by disposal and the migratory nature of the large swordfisli.
Disposal of acid wastes at this site should not significantly affect nekton
other than possibly causing them to avoid the affected area temporarily.
Alternative Sites
Conditions at the Northern and Southern areas are similar to the Acid Site,
and the same lack of effects would probably occur. Even if fish did avoid the
waste plume after disposal, this would only happen for an hour or so, until
the waste constituents are diluted to ambient levels.
4-12
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BENTHOS
Benthos consists of animals living on (epifauna) and in (infauna) the
sediments. Epifauna are dominated by larger echinoderms and crustaceans while
tne infauna primarily include small, segmented worms ( po lychaetes) and
mollusks. Benthic organisms are important as indicators of waste-related
impacts because many are seaentary and incapable of leaving a stressed
environment. They are also important because many are commercially valuable
(e.g., shellfish), or are food sources, such as worms, for valuable species
(demersal fish) .
Acid Site
The New York Bight benthos shows a natural temporal and spatial variability
substantially greater than any changes resulting from the disposal of acid
wastes (Pearce et al., 1976). Any effects from acid waste disposal would
probably be oversnadowed by effects from the numerous other contaminants
introduced to the New York Bight, particularly the Sewage Sludge and Dredged
Material Sites. This complex interplay between natural variability and
contaminants introduced by other sources makes it extremely difficult to
isolate and quantify effects at the site solely due to the disposal of acid
waste. All on-site investigations of the effects of waste disposal have led
to similar conclusions.
The first comprehensive study of the site by Reafield and WaLtoru (.
reported that, "biological observations have failed to produce any direct
evidence that the populations of fish or of bottom- living animals are being
damaged or excluded from the area by the disposal of waste." Vaccaro et al.
(1972) stated that "Our synoptic sampling was planned to detect alterations in
the biota of the acid grounds which could be attributable to discharge of
approximately 50 million tons of acid waste over a period of 22 years. We
have been unable to detect major effects of acid-iron waste on the sediment
and biotas ( phytoplankton, zooplankton, and benthos) of the region, although
we have indications in our observations of possible minor effects of this
waste." More recently, Swanson (1977) concluded that although "observational
evidence of the impact of dumping on the biota at the [sitej is limited...
4-13
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past studies indicate no reduction of primary productivity or phytoplankton
mortality...surveys of benthic populations in the immediate vicinity of the
Apex Acid Waste Dumpsite have not demonstrated an observable impact of waste
acid....existing scientific evidence indicates so far that ocean dumping lof
waste at the Acid Site] has had minor adverse impacts on the ecology."
106-Mile Site
No effects of chemical waste disposal have been observed in the oenthos at
the 106-Mile Site. The species composition and diversity at the site are .
similar to those observed in nearby Continental Slope areas (Pearce et ai.,
1975; Rowe et al., 1977). Analyses of trace metal content in benthic
invertebrates have shown values well within the range of background values
(Pearce et al., 1975). These results are not surprising since it is unlikely
that the low-density liquid waste could reach bottom in measurable concen-
trations. There is tremendous dilution due to the depth and movement of water
at the site. Tnerefore, readily-dispersed, low-density aqueous wastes should
not affect benthic organisms at or near the site.
Southern Area
The Southern Area benthos resembles that of the Delaware bay Acid Waste
Site (Figure 2-2, #9). Preliminary work indicated that disposal of acid
wastes at the Delaware Bay Acid Site caused measurable accumulation of
vanadium in the tissues of sea scallops (Pesch et al., 1977). Vanadium is not
known to be toxic to humans and probably does not nave an effect on the sea
scallops, yet this does show the possibility of accumulating other, more
toxic waste constituents. This would be an adverse long-term impact from acid
waste disposal. These effects are observable because of: (1) the relative
shallowness of the site (45 m), permitting some solid waste fractions to reach
bottom, (2) the lack of other contaminant inputs to obscure the effects of
waste disposal, (3) the presence of the shellfish, and (4) the ability of the
scallops to concentrate some metals in their tissues at levels much higher
than the levels in the surrounding water or sediment. Since the sites are
similar, especially the shallow-water depth factor, similar effects are
anticipated at the Southern Area if acid waste disposal is initiated.
4-14
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Accordingly, use of the Southern Area for disposal of acid wastes carries the
risk of contaminating commercially valuable shellfish populations, or
otherwise changing the benthic community structure.
Northern Area
Acid waste disposal at this site may have the same effects as at the
Delaware Bay or Southern Area Sites. Commercially exploitable snellfisn
resources, however, are not present at or near the site, thus the effects on
humans would be neglible. This site could be used for disposal if the benthos
is monitored carefully for changes related to the wastes.
WATER AND SEDIMENT QUALITY
ACID SITE
Investigations of the effects of waste disposal at the Acid Site have
continued for more than 30 years, but no changes in the water or sediment
chemistry have been positively linked to acid waste disposal. Tne New York
Bight Apex is a difficult region in which to assess impacts because of the
variety of contaminant sources and the existing nigh levels of most parameters
resulting from the populations and heavy industrialization of the region.
Most seawater measurements at the Acid Site are well within the background
values of the Bight Apex. Vaccaro et al. (1972) reported reduced surface
salinity at the site when compared with a control area. Turbidity is usually
greater at the site, caused by the iron-floe which forms wnen acid-iron waste
reacts with seawater (NOAA-MESA, 1975).
Trace metal (e.g., mercury, copper, lead, cadmium, and zinc) concentrations
in sedimenta have been reported. High metal concentrations in the Bight Apex
occur in the area of the nearby Dredged Material and Sewage Sludge Sites (Ali
et al., 1975). Values at the Acid Site are much lower than at other disposal
sites. Some workers have reported higher concentrations of trace metals in
Acid Site sediments than in sediments from supposedly uncontaminated areas
4-15
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(Vaccaro et al., 1972; EG&G, 1978c); however, these values have generally been
within the range of values from other locations in the Bight (SHL, 1972),
described below (Appendix B).
Ttie potential addition of disposal-related metals, on the "background"
levels at the Acid Site have been estimated (Table 4-2). Only zinc (U.04
tonnes/day) represents a significant input; but considering the total input of
zinc to the Apex (33 tonnes/day), any effects from the acid waste metal
content would not be measurable. The 14-day residence for water, used in the
calculations, is for the entire Apex. Water into which waste was released
moves from the site before the next disposal operation; therefore, the
calculations are extremely conservative.
Wastes presently permitted at the site satisfy criteria for evaluating
environmental impact (ERGO, 1978a,b), thus no significant changes in the
site's water quality are anticipated. Ambient concentrations of the waste
constituents are not exceeded beyond site boundaries. The concentrations
return to ambient levels within the period allowed for initial mixing (4
hours). In fact, except for the most abundant constituents (fluorides and
iron), concentrations usually return to ambient conditions within 1 hour.
There is one noticeable harmless change in the water quality at the site. The
ferric hydroxide floe which forms when acid-iron waste is released persists
for at least twelve hours (Charnell et al., 1974; ERGO, 1978c) and has been
reported to persist for several days (Vaccaro et al., 1972).
Continued use of the site for acid waste disposal will probably produce
similar results for measurements of the water and sediments. Background
values at the site of trace metals are in the milligrams-per-liter range.
Sample collection, storage, treatment, and analytical procedures can
accidentally introduce contamination, which affects analytical results,
Therefore, values slightly above background levels, resulting from disposal,
may be masked by the contamination introduced from sample handling.
Consequently, projections of disposal effects on the water and sediments must
be based on the present knowledge, allowing for the inherent weaknesses.
(This also applies to trace metal chemistry work at the other disposal sites).
4-16
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TABLE 4-2. WORST-CASE CONTRIBUTION OF WASTE METAL INPUT TO THE
TOTAL METAL LOADING AT THE NEW YORK BIGHT ACID WASTE DISPOSAL SITE
Background
Concentration
ug/ox
Total amount, (g)
in 7.7 x 10
liters
Estimated Input
(g) from 197b
Waste Volumes
and Mean
Concentrations
Estimated Input
in 7 Days
Percent of
Loading due
to Waste in
1 day
Cadmium
3.1
2.4 x 106
1.47 x 103
4.02 x 102
0.1
Copper
6.0
6.2 x 107
3.03 x 106
8.44 x 103
0.1
Lead
140
1.1 x 10*
1.25 x 106
3.42 x 103
0.1
Mercury
0.04
3.1 x 104
4.J x 10
1.18 x 102
0.1
Zinc
11.0
8.5 x 10b
1.52 x 107
4. It) x 104
0.5
Source:
* From Klein et al., 1974
t The total volume of the Site to 10-m depth
** The estimated flushing time for the Site (Redfield ana Walford, 1951)-
106-MILE SITE
A similar lack of effects is anticipated for the 106-Mile Site. Table 4-3
shows maximal metals additions due to acid waste, and the amounts are
insignificant ( 2/4 in all cases). Investigations of dissolved oxygen, pH,
organic carbon, and trace metals after waste disposal at the 106-Mile Site
have shown that within four hours after disposal the values are within the
normal range of values reported from this site and similar oceanic regions
(Hydroscience, 1977).
4-17
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TABLE 4-3. ESTIMATED WASTE METAL INPUT TO THE
TOTAL METAL LOADING AT THE 106-MILE SITE
Background
Concentration
Total Amount (g)
in 3.1 x 108
liters
Estimated Input
(g) from 197d
Waste Volumes
and i4ean
Concentrations
Estimated Input
**
in 14 Days ( g)
Percent of
Loading due to
Waste in 14 Days
Cadmium
J, 37
2.6 x 106
1.47 x 1U3
5.64 x 10J
O.U2
Copper
u.y
6.9 x 1U6
3.Ud x 1U°
1.18 x 1U3
1.7
Lead
2.9
2.2 x 1U7
1.25 x iUb
4.79 x 1U4
U.2
Mercury
J.72
5.5 x 10°
4.3 x 1U"3
1.65 x 1U2
U.I
Zinc
d.U
6.2 x 10
1 .:>2 x lu'
5.b3 x 1U5
u.y
Sources:
* From Hausknecht (1977)
t Tne volume of a quadrant of the site to 15-m depth
** The maximum length of time for residence of any water parcel in the
assuming a 10-cm/sec current and a 32 nmi (diagonal) distance across the
quadrant.
NOAA (1977) summarized the results of 1974 and 1976 investigations on trace
metals at the 106-Mile Site and at similiar nondisposal areas:
Results of the May 1974 cruise indicate that some metals were
significantly elevated compared to normal ambient concentra-
tions (Brezenski, 1975]. However, normal concentrations are
only a very few parts per billion, and great care must be
taken to avoid errors in measured values. A variety of fac-
tors can lead to misleading results, among them sample con-
tamination during collection, storage, or analysis. More
recent observations support the conclusion that heavy metal
concentrations in the...[site]...water column are typical of
shelf-slope regions [Kester et al., 1977; Hausknecht and
Kester, 1976ab]. Moreover, calculations show that the total
amount of metals added in dumping contributes less than 1
percent to the total normal amount of metals in the water at
4-18
-------
the dumpsite region [Hausknecht, 1977], None of the
observations occurred near the time of or in the immediate
vicinity of dumping, so that ambient concentrations would be
expected to be typical of the background for the region.
Therefore, investigations by NOAA and Hydroscience of effects from waste
disposal on the water chemistry of the site have not detected concentrations
elevated above ambient conditions after the initial mixing period.
Metal concentrations in sediments of the 106-Mile Site were measured in
1974 by Pearce et al. (1973). and in 1975 by Greig and Wenzloff U977J. The
metal concentrations reported tor 1976 are consistent with those for 1974.
Sediment metal concentrations varied little in samples from depths greater
than 180 m. Although the heavy metal content of sediments taken beyond the
Continental Shelf appears to be elevated relative to sediments on the
Snelf/Slope break, the elevated metal concentrations cannot be attributed to
present disposal practices at the 106-Mile Site, since they are not unique to
the site vicinity. Therefore, there is no evidence that the wastes released
at the site have affected the sediments (Pearce et al., 1973).
NORTHERN AMD SOUTHERN AREAS
The Northern and Southern Areas, which have never been used for waste
disposal, share a number of environmental features in common with the New York
Bight Acid Waste Disposal Site, except that they are deeper. Disposal of acid
wastes at these sites will probably have little effect on water chemistry, but
effects on the benthos (similar to those observed at the Delaware Bay Acid
Site) may occur. Such effects in the Southern Area would adversely affect
humans since exploitable shellfish exist near the site. It a new site were
established for acid waste disposal, the environmental consequences of
disposing the wastes would be much less in the Northern Area.
As with the Acid Site, the potential effects of disposal-related metal
input on the concentrations at these sites nave been estimated (Tables 4-4
and 4-5). Since the near-surface currents in these areas are quite strong
(16-20 cm/sec), and the residence time is short, acid waste constituents would
not measurably raise the ambient concentrations.
4-19
-------
TABLE 4-4. ESTIMATED WASTE METAL INPUT TO TOTAL METAL LOADING
AT THE SOUTHERN AREA
Metal Concentration
Background
Concentration
tug/ 1)
Total amount
(g) in
2.1 x 1012
liters
Estimated Input
(g) from Waste
Volumes and Mean
Concentrations
Estimated Input
in 2 Days (g)Tt
Percent of Loading
due to Waste in
2 days
Cadmium
1.6
3.4 x 106
s
1.47 x 10J
8.05 x 102
0.02
Copper
7.0
3.7 x 106
g
j.oa x 10
1.69 x 104
0.1
Lead
2.7T
1.7 x 105
f)
1.25 x 10°
6.85 x 10J5
0.1
Mercury
O.OdT
3.8 x 105
\
4,3 x 10
2.36 x 10
0.01
Zinc
18. J
3.8 x 10'
1.32 x lu
8.33 x iO^1
0.2
Sources:
* From NOAA,
t From EPA, 1976
** The volume of the site to 10 m depth
TT Based on the lowest observed current velocity at the site
EMERGENCY DUMPING
Ocean disposal regulations specify that, in emergency situations, tne
master of a transport vessel may discharge the waste load at any location and
in any manner to safeguard life at sea. Such emergency situations may result
from: (1) severe weather conditions that are typical in the North Atlantic in
late fail, winter, and early spring, and (2) vessel breakdowns, equipment
failure, or collisions with other vessels or stationary objects.
4-20
-------
TABLE 4-5. ESTIMATED WASTE METAL INPUT TO TOTAL METAL LOADING
AT THE NORTHERN AREA
Background
Concentration
Ug/ 1)
Total amount
(g) in
2.1 x 10i2
liters
Estimated Input
(g) from 1976
Wastes Volumes
and Me an
Concentrations
Estimated Input
in 2 Days ( g)
Percent of Loading
due to Waste in
2 Days
Cadmium
3.3
6.9 X 106
1.47 x 105
8.05 x 102
O.Ul
Copper
4.4
9.2 x 106
3.03 x 10b
1.69 x 104
0.2
Lead
2.7*
5.7 x 106
1.25 x 1U6
6.85 x 103
0.1
Mercury
o.Od
1.7 x iU5
4.3 x 103
6.85 x 10
0.01
Zinc
33. J
7.0 x 107
1.52 x 107
rf.33 x 104
0.1
Sources:
* From NOAA-MESA 1976
t From EPA, 1976
** Tne volume of the site to 10-m depth
tt based on the lowest observed current velocity at the site
The potential for illegal short dumping exists. The USCG ocean disposal
surveillance program discourages such illegal activities through a system of
shipriders, patrol vessels, aircraft overflights, and checking of vessel logs.
The procedures for administering ocean dumping permits also discourage these
activities by requiring notification of departures and commencement of
disposal, providing overlays of the barge's track, and examining snips' logs.
If violations do occur the permit provides for civil and criminal penalties
ranging from revocation of the permit to a $50,000 fine.
Twenty-four possible violations of permit regulations sufficient to cause
follow-up actions were reported to EPA-Region II between 1973 ana 1977. Three
were for the Acid Site and seven were for the 106-Mile Site. Of the three
4-21
-------
violations at the Acid Site, one was upheld and a civil penalty assessed;
had the charges withdrawn, and one is pending (.EPA, 197daj . At the lOO-toi
Site, four citations were upheld and civil penalties assessed, one was
dismissed, and two had the charges withdrawn. Ho enforcement actions were.
initiated against permittees at either site in 1^73 (.EPA,
Tne probability of an emergency rises as the round^trip transit time
increases. (See Table 4-1 tor estimated transit times.*. The decision to
locate a site far from shore carries with it the increased risk of emergencies
resulting in short dumping. The effects of a short dump of toxic waste
materials would depend on the Location of the dump. Since acid wastes are
liquid and rapidly diluted upon discharge, a single load of waste in a new
area might cause local immediate acute effects, but should not cause any
long-term adverse effects. Effects of emergency dumping during inclement
weather would be mitigated by the rapid dilution caused by storm activity.
Use of any of the alternative sites involves the possibility of legal or
illegal short dumping. Based on distance of a site from port, the probability
of a short dump is highest for the 106-Mile Site and lowest for the Acid Site.
Except for the Acid Site, however, tne effects of a snort dump would be
short-term and the ecosystem would rapidly recover, Short dumping at the Acid
Site causes more concern because of close proximity to shore and the
possibility of waste constituents reaching the New Jersey or Long IslancJ
shorelines .
UNAVOIDABLE ADVERSE ENVIRONMENTAL
EFFECTS AND MITIGATING MEASURES
Some unavoidable adverse environmental effects of disposal of liquid acid
wastes will occur in all sites designated. Field and laboratory observations
show the most important short-term adverse impacts to be:
• Acute mortality in plankton
• Rise in waste constituent concentrations in the water
• Lowering of pH
• Possible avoidance of the area by fish
4-22
-------
These effects occur immediately upon release of the wastes, but do not
persist beyond the period allowed for initial mixing.
The most important potential long-term adverse impacts are:
• Possible accumulation of waste constituents by the benthos in
shallow waters
• Sublethal effects on zooplankton and fish. These have been ooserved
only in the laboratory at higher waste concentrations than occur at
the site.
The volumes and rates of waste discharges specified in disposal permits
have been established to reduce possibility of short-term effects persisting.
The continuous monitoring program, by permittees and the Federal government,
was established to determine if short-term or long-term effects are occurring.
None of the effects described in this section apparently persist for more
than a few hours after the waste is discharged; consequently, none of these
impacts are irreversible and additional mitigating measures are not required.
RELATIONSHIP BETWEEN SHORT-TERM USE
OF THE SITE AND LONG-TERM PRODUCTIVITY
For some of the alternative sites, there appears to be conflict between the
short term use of the area as a waste disposal site and the area's long term
productivity as part of the mid-Atlantic bight ecosystem. Exploitable
shellfish and possible mineral resources in the Southern Area bite would cause
conflict. Adverse effects are probably reversible, but it is not certain.
Neither the 106-Mile Site nor the Northern Area Site appear to offer conflicts
between short-term use and long-term productivity. The Northern Area Site is
more likely to show any adverse effects than the 106-Mile Site since it is
closer to shore and shallow.
The Apex of the New York Bight is affected, by many waste inputs, and
additional released wastes would not be readily detected. For the long-term,
these wastes could exceed the total assimilative capacity of the New York
4-23
-------
big lit Apex. However, continual monitoring should detect any changes, and
the permitting authority for the site, can halt or modify disposal practices
at the site. The magnitude of the contaminant inputs from acid waste must be
kept in perspective; ttiey are generally less than the inputs from tne
atmosphere. Acid waste disposal activities at this site over the past; 3D
years have not interfered with shipping, fishing, recreational activities, or
the development of other resources. There is no evidence that the long-terip
productivity of the area has been adversely affected by the wastes.
IRREVERSIBLE OR IRRETRIEVABLE
COMMITMENTS OF RESOURCES
Several resources will be irreversibly or irretrievably committed by the
proposed action:
• Loss of energy (i.e., fuel for transporting barges to and from the
site). Transport to distant sites requires more fuel,
• Loss of constituents in the waste, (e.g., acids or metals).
Present-day technology or markets are not adequate to permit
economical recovery.
• Loss of economic resource due to costs associated witn ocean
disposal. Ocean disposal costs, however, are almost always lower
than the costs of land-based disposal methods.
4-24
-------
Chapter 5
LIST OF PREPARERS
Preparation ot this EIS was a joint effort employing many members of the
Interstate Electronics Corporation scientific and technical staff. This
chapter summarizes the background and qualifications of the primary workers on
the document (Table 5-1).
The principal author wishes to thank those people who assembled background
information, wrote or commented upon short sections, and performed the data
analysis for the EIS. The document has benefited greatly from their
assistance.
TABLE 5-1. LIST OF PREPARERS
Responsible
Person
M. Hoi strom*
R. Lewis
B. Knudtson
K. King
Summary
A
Chapter
1
A
2
A
3
A
4
A
5
A
Appendix
A
A
A
B
A
A
C
A
D
A
E
A
*EIS Coordinator and principal author
A=Author
MARSHALL HOLSTROM
Mr. Holstrom is the principal author of the EIS. He is a marine biologist
and staff EIS coordinator within the Biological Sciences Branch of the
5-1
-------
contractor's Oceanic Engineering Division. He holds B.A. and M.A. degrees in
Biological Sciences from Stanford University and has completed additional
graduate work in marine biology at the University of Southern California.
Mr. Hoistrom prepared the Summary; Chapters 2, 3, 4, and 5; and Appendices
A, B, and E. As the coordinator for this EIS, he directed the writing eff9rts
on other sections, edited the entire document, and maintained liaison with
EPA Headquarters and EPA-Region II.
ROBIN LEWIS
Mr. Lewis, a biological oceanographer at Interstate received his B.S.
degree in Marine Biology from California State University, Long Beach, and is
presently a candidate the M.S. degree.
Mr. Lewis prepared Appendixes C and D of this EIS and performed the
analyses of the waste loading data.
BRUCE KNUDTSON
Dr. Knudtson obtained his B.A. from the University of California, Santa
Barbara, and his M.S. and Ph.D. from the University of Southern California.
Dr. Knudtson assisted in writing Appendixes A and B and performed some pf
the analyses used to evaluate alternative disposal sites.
KATHLEEN M. KING
Ms. King is a marine biologist holding the B.S. in Biological Scienc.es from
the University of California and an M.A. in Biology (with emphasis on marine
biology) from California State University, Long Beaqh.
Ms. King prepared Chapter 1 of this EIS.
5-2
-------
Chapter 6
GLOSSARY AND REFERENCES
GLOSSARY
Abundance
Abyssal
Acute effect
Adsorb
Aesthetics
Alkalinity
Ambient
Amphipods
Anaerobic digestion
Anthropogenic
Anticyclonic
Anticyclonic eddies
The number of individuals of a species
or taxon inhabiting a given area.
Pertaining to the great depths of tne
ocean beyond the limits of the
continental slope, from 2,000 to
5,000 m.
The death or incapacitat ion of an
organism caused by a substance within a
short time (normally 96 hours).
To adhere in an extremely thin layer of
molecules to the surfaces of solid
bodies.
Pertaining to the natural beauty or
attractiveness of an object or location.
in
of anions of weak acids _
plus hydroxide ions (OH ),
hydrogen ion (H ) concen-
Alkalinity is usually
The sum
seawater,
minus the
trations.
calculated by the empirical equation
meq/kg = 0.061 x salinity (g/kg).
Pertaining to the undisturbed or
unaffected conditions of the surrounding
environment.
A large order of predominantly marine
crustaceans, ranging from free-living,
planktonic forms to benthic, tube-
dwelling forms, which usually have
laterally compressed bodies (sand fleas,
etc.).
Digestion of organic matter by
bacterial action in the absence of
oxygen.
Relating to the effects or impacts of
man on the ecosystem.
A rotation about the local vertical that
is clockwise in the Northern Hemisphere.
Mesoscale (50 to 100 km) features of
oceanic circulation in which water flows
in a circular (clockwise) pattern around
warm core waters.
-------
Apex
See New York Bight Apex.
Appropriate sensitive
benthic marine
organisms
Appropriate sensitive
marine organisms
Aqueous
Assemblage
Background level
Baseline data
Baseline surveys
Benthos
Bight
Bioaccumulate
Species representing different feeding
types ( filter-feed ing, deposit-feed ing,
and burrowing) , chosen from the most
sensitive species accepted by EPA as
being reliable test organisms to
determine the anticipated impact on the
site.
At least one species each, represen-
tative of phytoplankton or zooplankton,
crustacean or mollusk, and fish species
chosen from tne most sensitive species
documented in the scientific literature,
or accepted by EPA as being reliable
test organisms to determine the
anticipated impact of the wastes on the
ecosystem at the disposal site.
Similar to, containing, or dissolved in
water.
A recurring group of organisms having a
common habitat.
The naturally occurring (or ambient)
level of a substance within an
environment.
Data collected prior to the initiatipn
of actions which have the potential of
altering an existing environment.
Surveys conducted to collect information
prior to the initiation of actions which
have the potential of altering an
existing environment.
All marine organisms (plant or animal)
living on or in the bottom; also, the
floor of the ocean.
A slight indentation or bend in shore-
line, river, open coast, or bay.
The intake and assimilation of
materials, e.g., heavy metals, leading
to an elevated concentration of the
substance within an organism's tissue,
blood, or body fluid.
6-2
-------
Bioassay
Biochemical Oxygen
Demand (BOD)
Biomass
Biota
Biotic groups
BLM
Bloom
Boreal
°C
C/N
Carcinogen
CE
Cephalopoda
CFR
Chaetognaths
Chlorophyll
Determination of the strength (potency)
of a substance by its effect (on growth
or survival) upon an organism—plant or
animal.
The amount of oxygen consumed by
microorganisms while assimilating and
oxidizing organic (and some nitrogenous)
materials in water or wastewater under
specified environmental conditions and
time periods.
The amount (weight) of living organisms
inhibiting a given area or volume.
Collectively, plants and animals of a
reg ion.
Organisms which are ecologically.
structurally, or taxonomically grouped.
Bureau of Land Management.
Relatively high concentrations of
plankton in water resulting from their
rapid growth and reproduction.
Pertaining to the higher northern
latitudes, as opposed to tropical.
Degrees Celsius, formerly centigrade.
Carbon/nitrogen ratio.
A substance or agent producing cancer.
U.S. Army Corps of Engineers.
Squid, octopus, or cuttlefish. Members
of the phylum Mollusca.
Code of Federal Regulations.
A phylum of small, elongate, free-
swimming transparent, woruilike
invertebrates, also known as arrow-
worms, which are important carnivores in
the zooplankton community, with chaetae
(bristles) curved on each side of the
mouth.
A group of green plant pigments which
function as photoreceptors of light
energy for photosynthesis.
6-3
-------
Chlorophyll £
Chronic effect
cm
cm/ sec
Coccolithophorid
Coelenterate
Compensation depth
Continental margin
Continental Rise
Continental Shelf
Continental Slope
Contour line
Copepod
A specific green plant pigment used in
photosynthesis, and used as a measure of
phytoplankton biomass.
A sublethal effect of a substance on an
organism which reduces the survivorship
of that organism after a long period of
exposure to low concentrations of the
substance.
Centimeter(s).
Centimeters per second.
Ultra-microscopic planktonic algae, the
cells of which are surrounded by an
envelope of small calcareous discs.
A animal phylum which includes hydroids,
sea anemones, jellyfish, and corals.
The depth at which photosynthetic oxygen
production equals oxygen consumed by
plant respiration.
The zone between the shoreline and the
deep ocean floor; generally consists of
the Continental Shelf, Continental
Slope, and the Continental Rise.
A transitional portion between the
Continental Slope and the ocean floor
which is less steeply sloped than the
Continental Slope,
The continental margin extending seawar4
from the coast to a variable depth,
generally 200 m.
The steeply descending slope lying
between the Continental Shelf and the
Continental Rise.
A chart line connecting points of equal
depth above or below a reference plane,
generally sea level.
A large subclass of usually small
crustaceans; they are an important link
in the oceanic food chain.
6-4
-------
Coriolis effect
An apparent force acting on moving
particles resulting from the earth's
rotation. In the northern hemisphere
moving particles are deflected to the
right, and in the southern hemisphere to
the left.
Crustaceans
Ctenophores
Cuesta
Current meter
Current shear
Animals with jointed appendages and a
segmented external skeleton composed of
a hard shell (chitin). The group
includes barnacles, crabs, shrimps, and
lobsters, co v-. pods, and amphipods.
An animal phylum superficially
resembling jellyfish, ranging from less
than 2 cm to about 1 m in length. These
planktonic organisms are commonly
referred to as comb jellies or sea
walnuts.
An asymmetrical ridge with one slope
gentle and the other steep.
Any device for measuring and indicating
flow rate, velocity, or direction (often
all three) of flowing water.
The measure of the spatial rate of
change of current velocity with units of
cm-sec/sec/m .
Decapod
Demersal
Density
Diatom
The largest order of crustaceans in
which the animals have five pairs of
locomotory appendages, each joined to a
segment of the thorax. Includes crabs,
lobsters, and shrimp.
Living at or near the bottom of the sea.
Applies mainly to fish.
The mass per unit volume of a substance.
Single cell, usualy planktonic plant
with a cell wall of silica. Abundant
world wide.
Diffusion
The process whereby particles in a
liquid intermingle spontaneously; net
motion is from an area of higher
concentration to an area of lower
concentration.
6-5
-------
Dinoflagellate
Discharge plume
Dispersion
Dissolved oxygen
Dissolved solids
Diversity
Dominance
Dry weight
EC
50
Echinoderms
Economic resource
zone
Single-celled, planktonic organisms with
flagella, which are an important part ot
marine food chain.
The region of seawater affected by a
discharge of waste which can be
distinguished from the surrounding
water.
The movement of discharged material over
large areas by the natural processes of
mixing (turbulence and currents.).
The quantity of oxygen dissolved in a
unit volume of water; usually expressed
in mg/liter.
Solid matter in solution, such as salt
dissolved in water.
A measure that usually takes into
account the number of species and the
relative abundance of individuals in an
area.
A species or group of species which
strongly affect a community because of
their abundance, size, or control of
energy flow.
The weight of a sample of materials
and/or organisms after all water has
been removed; a measure of biomass.
In bioassay studies, the concentration
of a substance which causes a 50 percent
reduction in the growth rate of the test
organisms (usually phytoplankton) during
a unit time (usually 96 hours).
A phylum of benthic marine animals
having calcareous plates and spines
forming a rigid articulated skeleton or
plates with spines embedded in the skin.
This group includes starfish, sea
urchins, sea lilies and sea-cucumbers.
The oceanic area within 200 nmi from
shore in which the adjacent coastal
state possesses exclusive rights to the
living and non-living marine resources.
6-6
-------
Ecosystem
Eddy
EIS
Endemic
Entrain
EPA
EPA Region II
Epifauna
Epipelagic
Estuary
Euphausiids
°F
Fades
Fauna
FDA
Flagellum (pi. -a)
A functional system which includes the
organisms of a natural community or
assemblage together with their physical
environment.
A generally circular water current
moving contrary to the direction of the
main current.
Environmental impact statement.
Restricted or peculiar to a locality or
region.
To carry along with (e.g., eddies
entrain other waters).
U.S. Environmental Protection Agency
U.S. Environmental Protection Agency,
Region II, New York, N.Y.
Animals which live on the surface of the
sea bottom.
Ocean zone extending from the surface to
200 meters in depth.
A semienclosed coastal body of water,
which has a free connection to the sea
and within which the sea water is
measurably diluted with fresh water.
Shrimp-like, planktonic crustaceans
which are widely distributed in oceanic
waters. These organisms, also known as
krill, may grow to 8 cm in length and
are an important link in the oceanic
food chain.
Degrees Fahrenheit.
Any observable attribute of a
stratigraphic unit, such as overall
appearence or composition.
The animal life of a particular
location, region, or period.
Food and Drug Administration.
Whip-like appendage(s) used for
swimming.
6-7
-------
Flocculate
Flora
FWPCA
3
g/cm
Gangue
Gastropods
Geostrophic current
Gulf Stream
Heavy metals or
elements
High-level radioactive
waste
Histopathology
H1values
The process of aggregating a number of
small, suspended particles into small
masses.
The plant life of a particular location,
region, or period.
Federal Water Pollution Control Act.
Grams per cubic centimeter.
Mineral matrix, useless rocks.
Mollusks that possess a distinct head
(generally with eyes and tentacles) and
a broad, flat foot, and which usually
have a spiral shell (snails, etc.).
A stable current due to gravitational
forces and the Coriolis force.
A warm, swift, northward flowing ocean
current flowing through the Caribbean,
Gulf of Mexico and up the North American
East Coast.
Elements with specific gravities of 5P0
or greater.
The aqueous or solid wastes from repro-
cessing irradiated fuel of nuclear power
reactors.
The study of tissue changes associated
with disease.
Shannon-Wiener species diversity index.
Hydrography
Ichthyoplankton
IEC
Indigenous
Infauna
In situ
The measurement and description of the
physical features of bodies of water.
Fish eggs and weakly motile fish larvae.
Interstate Electronics Corporation.
Having originated in and being produced,
grown, or naturally occurring in a
particular region or environment.
Animals which live or burrow below the
sea bottom.
(Latin) in the original or natural
setting.
6-8
-------
Insolation
Invertebrates
ISC
Isobath
kg
kg/day-
ton
kn
LC5Q (Lethal
concentration 50)
Limiting permissible
concentration (LPC)
Lor an- C
m
m3
m/sec
Macrozooplankton
Marine
Solar radiation received at the earth's
surface.
Animals without backbones.
Interstate Sanitation Commission.
A line on a marine chart joining points
of equal depth below sea level.
KilogramC s).
Kilograms per day.
KilometerC s).
Knot(s), nautical miles per hour.
In bioassay studies, the lethal concen-
tration (LC) of a substance which causes
50 percent mortality in the population
of the test organisms during a given
time (usually 96 hours).
A concentration of a waste substance
which after initial mixing, does not
exceed marine water quality criteria or
cause acute or chronic toxicity.
Long Range Aid to Navigation (Type C) .
Meter(s).
Cubic meters.
Meters per second.
Micron(s), 10 m.
Micrograms per kilogram, or millionth
gram per kilogram.
Micrograms per liter, or millionth gram
per liter.
Micron, micrometer, millionth of a
meter.
Planktonic animals which can be seen by
the unaided eye.
Pertaining to the sea.
6-9
-------
Massif
Mesopelagic
mg
MGD
mg/1
mi
Micron
Microorganisms
Mid-Atlantic Bight
Mixed layer
ml
ml/m2/hr
puro
Monitoring
mph
MPRSA
Mutagen
Myctophids
A mountainous mass or group of connected
heights, more or less clearly marked off
by valleys (land or submarine).
Relating to depths of 200 to 1,000 m
below the ocean surface.
Milligram(s), or thousandthCs) gram.
Million gallons per day (3,785 million
liters per day).
Milligrams per liter.
Mile(s) , 5,280 ft.
Millionth(s) of a meter.
Microscopic organisms including
bacteria, protozoans, and some algae.
The Continental bhelf extending from
Cape Cod, MA. to Cape Hatteras, NC.
The upper layer oi tue ocean wuicu it
well mixed by wind and wave activity,
Killiliter(s) , or tnousandth(s) liter.
Milliliter(s) per square meter per hour.
Millimeter(s), or thousanatn(s) meter.
As used herein, to observe environmental
effects of disposal operations through
biological, chemical, geological, and
physical data collection and analyses.
Miles per hour.
Marine Protection, Research, and
Sanctuaries Act.
A substance which increases the
frequency or extent of mutations.
A group of small mesopelagic fish which
possess light-emitting organs and
undergo large-scale vertical (deep to
near-surface) migrations daily.
6-10
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Nannoplankton
NAS
NASA
Nekton
NEPA
Neritic
Neuston
New York Bight
New York Bight Apex
NJDEP
nmi
NOAA
NOAA-MESA
NOAA-NMFS
NSF
Minute planktonic plants and animals
which are 50 microns or less in size.
Individuals of this size will pass
through most plankton nets and are.
therefore usually collected by
centrifuging water samples.
National Academy of Science.
National Aeronautics
Administration.
and Space
Free swimming animals which
independently of water currents.
move
National Environmental Policy Act of
1969.
Pertaining to the region of shallow
water adjoining the seacoast and
extending from low-tide mark to 2UO m
depth.
A community of planktonic organisms
which are associated with the surface
film of water; mainly composed of
certain copepods and the eggs and larvae
of fish.
The continental shelf which extends from
Montauk Point, Long Island to Cape May,
New Jersey.
A portion of the New York Bight bounded
at the south by latitude 40°10'N and at
the east by longitude 73°30'W.
New Jersey Department of Environmental
Protection.
Nautical mile(s), 6,060 ft or 1.852 km.
National Oceanic and Atmospheric Admini-
stration.
National Oceanic and Atmospheric Admini-
stration-Marine EcoSystems Analysis.
National Oceanic and Atmospheric Admini-
stration-National Marine Fisheries
Service.
National Science Foundation.
6-11
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Nuisance species
Nutrient
OCS
ODSS
Organophosphate
Pesticides
Ortho-phosphate
Oxygen minimum layer
Parameters
Particulates
Parts per thousand
(ppt; o/oo)
Pathogen
PCB('s)
Pelagic
Perturbation
PH
Organisms with no commercial value which
outcompete, oust, or harm commercially
important species.
Any substance which promotes growth or
provides energy for biological
processes.
Outer Continental Shelf.
Ocean Dumping Surveillance System.
A phosphorus-containing organic pest-
icide, such parathion or malathion.
One of the possible salts of ortho-
phosphoric acid, an essential nutrient
for marine plant growth.
The depth in the water column where the
lowest concentration of dissolved oxygen
naturally occurs.
Any of a measurable set of physical,
geological, chemical, or biological
properties whose values determine the
characteristics of the area under
certain conditions.
Fine solid particles which
individually dispersed in water.
are
A unit of concentration of a mixture
indicating the number of parts of a
constituent contained per thousand parts
of the entire mixture.
Producing or capable of producing
disease.
Polychlorinated biphenol(s).
Pertaining to water of the open ocean
beyond the shore and above the abyssal
zone.
Disturbance of a natural or regular
system.
Numerical range (0-14) used to describe
the hydrogen ion activity; 0-7 is acid,
7 is neutral, 7-14 is alkaline,
6-12
-------
Photic Zone
Phytoplankton
Plankton
Polychaetes
ppb
ppm
ppt
Precipitate
Predator
Primary Production
Protozoa
Qualitative
Quantitative
Recruitment
Redox potential
The layer in the ocean from the surface
to the depth where light is reduced to
1.0% of its surface value.
Planktonic plants; the base of most
oceanic food chains.
Passively floating or weakly motile
plants or animals in a body of water.
The largest class of the phylum Annelida
(segmented worms) distinguished by
paired, lateral, fleshy appendages
provided with setae on most segments.
Parts per billion.
Parts per million.
Parts per thousand.
A solid which separates from a solution
or suspension by chemical or physical
means.
A carnivorous animal which uses other
animals as a source of food.
The amount of organic matter synthesized
by plants from inorganic substances per
unit time per unit area or volume. The
plant's respiration may (net produc-
tivity) or may not (gross productivity)
be subtracted.
Microscopic, single-celled organisms of
extremely diverse characteristics.
Pertaining to the nature, being,
attribute, trait, character, or status.
Pertaining to the numerical measurement
of a parameter (quantity, mass, extent,
range).
Addition to a population of organisms by
reproduction or immigration of new
individuals.
Measurement of the state of oxidation of
the system.
6-13
-------
Release zone
Runoff
An area 100 meters on either side of the
disposal vessel extending from the point
of first waste release to the end of the
release.
That portion of total surface precip-
itation on land that ultimately reaches
streams or the ocean.
Salinity
Sea state
sec
Shelf water
Shellfish
Shiprider
Short dumping
Significant wave
height
Slope water
Sludge
Species
The amount of dissolved salts in
water usually measured in parts per
thousand.
The numerical or written description of
ocean roughness.
SecondC s).
Water which originates in or can be
traced to the Continental Shelf. It has
characteristic temperature and slainity
values which identify it.
Any aquatic invertebrate having a shell
or exoskeleton, especially any edible
mollusk or crustacean.
An observer aboard a vessel, assigned by
the Coast Guard to ensure that ocea,n
disposal operations are conducted
according to permit specifications.
The premature discharge of waste from a
vessel anywhere outside designated
disposal sites. This may occur legally
under emergency circumstances or
illegally to avoid hauling to a
designated site.
The average height of the one-third
highest waves in a given wave group.
Water which originates from, occurs at,
or can be traced to tne Continental
Slope. It has characteristic;
temperature and salinity values whicki
identify it.
Precipitated solid matter from sewage
and chemical waste treatment processes.
A group of individuals which closely
resemble each other structurally and
physiologically and interbreed in
nature, producing fertile offspring.
6-14
-------
Specific gravity
SPM
sq
SS
Standing stock
Stressed
Surfactant
Surveillance
Suspended solids
Synergism
Taxon (pi. taxa)
TCH
Temporal distribution
Teratogen
Terrigenous sediments
The ratio of the density of a substance
relative to the density of pure water at
4°C.
Suspended particulate matter.
Square.
Suspended solids.
The biomass or abundance of living
material per unit volume or area of
water.
A stimulus or series of
disrupt the normal
functions of an area.
stimuli which
ecological
An agent which lowers surface tension of
a liquid, (in water - soap, bile and
certain detergents).
Systematic observation of an area by
visual, electronic, photographic, or
other means for the purpose of ensuring
compliance with applicable laws,
regulations and permits.
Finely divided particles of a solid
temporarily suspended in a liquid, e.g.,
soil particles in water.
The interaction between two or more
agents which produces a total effect
greater than the sum of the independent
effects.
A group or entity sufficiently distinct
to be distinguished by name and to be
ranked in a definite :ategory (adj.
taxonomic).
Total carbohydrate content.
The distribution of a parameter over
time.
A chemical agent which causes
developmental malformations and
monstrosities.
Shallow marine sedimentary deposits
composed of eroded terrestrial material.
6-15
-------
Thermocline
TKN
TOO
Trace metal or
element
Trend assessment
Surveys
Trophic level
Turbidity
Turnover rate
USCG
Water mass
Water type
Wet weight
yd3
Zooplankton
A sharp temperature gradient which
separates a warmer surface water }.ayer
from a cooler subsurface layer, most
pronounced during summer months.
Total Kjeldahl nitrogen.
Total organic carbon.
An element found in the environment in
extremely small quantities.
Surveys conducted over long time
periods to detect shifts in environ-
mental conditions within a region.
A feeding level in the food chain of an
ecosystem through which the passage of
energy proceeds,
A reduction in transparency which, in
seawater, may be caused by suspended
sediments or plankton growth.
The time necessary to replace the entire
standing stock of a population;
generation time.
U.S. Coast Guard.
A body of water usually identified by
its temperature, salinity and chemical
content and containing a mixture of
water types.
Water defined by a narrow range of
temperature and salinity.
The weight of organisms before drying
them to remove the internal water.
Cubic yard(s)
Usually small, passively floating or
weakly swimming animals which are
important in many marine food chains.
6-16
-------
UNITS OF MEASURE (ENGLISH EQUIVALENTS OF METRIC UNITS)
Metric
centimeter (cm)
meter (m)
kilometer (km)
2
square meter (sq m; m )
o
square kilometer (sq km; km )
gram (g)
kilogram (kg)
metric ton (tonne)
liter (1)
o
cubic meter (cu m; m )
English
0.4 inches (in)
1.1 yards (yd)
0.62 statute miles (mi)
0.54 nautical miles (nvni)
1.2 square yards (sq yd; yd )
0.29 square nautical miles (sq nmi; nmi'*j
0.035 ounces (oz)
2.2 pounds ( Ib)
1.1 short tons; (short ton = 2,000 Ib)
0.26 gallons (gal)
2
1.3 cubic yards (cu yd; yd )
• 2
centimeters/second (cm/sec)
kilometers/hour (km/hr)
0.39 inches/second (in/sec)
0.54 knots (kt), nautical miles/hour
celsius (°C)
(9/5 °C + 32) Fahrenheit (°F)
6-17
-------
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6-22
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6-34
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.,
6-41
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Appendix A
NEW YORK ACID SITE
-------
CONTENTS
Page
METEOROLOGY A-l
PHYSICAL OCEANOGRAPHY . . • A-4
Water Types A-5
Current Regimes ....... A-6
Temperature Distribution ...... A-6
Salinity Distribution ... A-8
Waves and Winds k A-^
GEOLOGY A-ll
Bathymetry , A-ll
Sediment Types A-13
Suspended Particulate Matter , A-1J
Grain Size A-15
Transport A-15
CHEMICAL OCEANOGRAPHY A-16
Water Column ..... A-l7
Sediments A-20
Biota A-21
BIOLOGICAL CHARACTERISTICS , . . t A-22
Water Column A-23
Benthos A-2y
ILLUSTRATIONS
A-l Frequency of Waves on a Percentage Basis from Month to Month .... A-10
A-2 Morphologic Framework of the New York-New Jersey Shelf A-12
A-3 Distribution of Surficial Sediment Based on Visual
Sample Examination. Bathymetry from 1936 Data A-14
A-4 Area Closed to Shell fishing in the New York Bight A-30
A-5 Benthic Faunal Types in the Mid-Atlantic Bight A-31
A-i
-------
TABLES
Table Page
A-l Incidence of Fog in the New York Bight , A-*3
A-2 Icing Conditions in the New York Bight , . AH
A-3 Average Precipitation per Month A"4
A-4 Mean Trace Metal Levels in the Unplotted Seawater Samples ..... A~|9
A-5 Mean Traca lietal Concentrations in the New York Bight ........ A-19
A-6 Phytoplanktpn Species with Cell Densities Greater than
Ten Thousand per Liter in the New York Bight . , , A-24
A-7 Seasonal Occurrence of Zooplankton in the New York Bight Apex ... A-27
A-8 Benthic Species Characteristic of the Sand Fauna in the
Middle Atlantic Bight A~32
A-ii
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Appendix A
ENVIRONMENTAL CHARACTERISTICS
OF THE NEW YORK BIGHT
An understanding of the oceanographic features of the New York Bight is
essential for an evaluation of the effects of acid waste disposal. The Bight
is adjacent to the most heavily populated, highly industrialized section of
the eastern seaboard, and is a heavily used and environmentally "stressed"
coastal area. It receives wastes from 20 million people and a number of major
industries. Municipal and industrial wastewater effluents, urban runoffs,
atmospheric fallout, and materials dispersed at different dumpsites add large
quantities of heavy metals, nutrients, organic matter, and chlorinated
hydrocarbons to the Bight waters. The Bight supports important commercial and
recreational fisheries and other activities (MESA, 1977).
Records are extensive for the region. The MESA New York Bight Atlas ana
Monograph series describe the area excellently. Other MESA-sponsored works
exist as data reports, technical reports, and technical memos (MESA, 1978b).
A detailed technical summary resulted from a symposium (Gross, 1976c)
sponsored by the American Society of Limnology and Oceanography in November
1975. Earlier, workers from the Atlantic Oceanographic and Meteorological
Laboratory had assessed the nonbiological aspects of the Bight (Charnell,
1975).
METEOROLOGY
Seasonal meteorological events affect man's use of the New York Bight for
waste disposal, shipping, resources, and recreation. Meteorology is an
important influence on physical characteristics of the area, which determine
dispersion of wastes. Sufficient knowledge and predictability of meteorology
exist to permit site designation for waste disposal, with minimal danger to
workers on disposal operations. Excellent sources for the conditions in the
Bight are Williams and Godshell (1977), Mohnen (1977), and Lettau et al.
(1976).
A-l
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WINDS AND STORMS
Winds
Bryson and Lahey (1958) defined the natural seasons of the New York Bight
as winter (November to March) and summer (July to August) . Wind speeds are
usually moderate. During the winter, winds are offshore breezes with average
speeds of 9 to 13 kn while summer winds are onshore with average speeds of 5
to 9 kn. Strong winds (between 28 and 40 kn) are more common in the winter
(10% of all observations) than in summer (1% of all observations) but strong
winds (greater than 40 kn) have occurred during Qvery month.
Highest recorded winds for New York Bight were due to tropical storms. In
1960, wind speeds recorded from hurricane Donna were 6J. kn (70 mph) from the
northeast at La Guardia Airport; wind speeds of 98 kn (113 mph) from hurricane
Hazel were recorded at The Battery in 1954 (Lettau et al., 1976).
Storms
Seasonal storms are characteristic of the New York Bight area. Extra-
tropical (northeasterly) storms are common from November until April (Pore,
Richardson, and Perroth, 1974) while tropical storms (hurricanes) usually
occur in the late summer or early autumn (Pore and Barrientos, 1976). Pore
and Barrientos (1976) reported that an average of 6.8 storms per year cause
moderate to severe coastal damage. The recorded frequency of northeasters (10
to 14 days) is greater than hurricanes (4 to 7 years). Storms may restrict a
particular disposal operation, but frequencies or severities are not
sufficient to restrict all disposal operations.
VISIBILITY
Visibility in the New York Bight is influenced by fog, smoke, and haze.
Thick fogs occur, but not frequently enough to restrict sailing to ana from
the site.
A-2
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F_og
The maximal incidence of fog occurs from May to July, when the greatest
differences between sea and air temperatures exist. Fog is not generally
frequent between October and March, but heavy fogs occasionally occur. The
monthly frequency of restricted visibility in the New York Bight is summarized
in Table A-l.
TABLE A-l. INCIDENCE OF FOG IN THE NEW YORK BIGHT
T i m i t n -F
Visibility
1/4 Mile
1 Mile
Average Days/Month
Jan
1.1
4.2
Peb
0.8
3.6
Mar
3.3
5.6
Apr
0.8
3.0
May
7.4
11.5
Jun
4.0
7.7
Jul
4.6
6.6
Aug
0.3
4.2
Sep
0.6
3.0
Oct
1.9
3.3
Nov
1.8
2.9
Dec
0.5
1.6
Source: Modified from Williams and Godshall, 1977.
When necessary, disposal operations can be performed under conditions of
restricted visibility and fog, smoke or haze (see below), and these do not
constitute important factors which restrict use of sites in New York Bight.
Smoke and Haze
Smoke is an anthropogenic product, and its effects decrease offshore, haze
often comprises dust and salt particles, and haze frequencies are evenly
distributed over the Bight. Maximal peaks of haze are associated with
southwesterly winds, while minimal values are usually recorded when there are
northwesterly winds (Lettau et al., 1976). Neither smoke nor haze signifi-
cantly restrict navigation in the Bight area.
AIR TEMPERATURE
Air temperatures in the New York Bight range from a mean low of 2°C (36°F)
in February, to a mean high of 22°C (approximately 72°F) in August (Lettau et
al., 1976). Only a slight icing potential occurs between December and March
(Table A-2).
A-3
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TABLE A-2. ICING CONDITIONS IN THE NEW YORK BIGHT
Icing Potential
Light
Moderate
Percent Per Month
Dec
Jan
4.8
0.9
Feb
6.2
0.3
Mar
1.3
Source: Modified from Williams and Godshall, 1977,
PRECIPITATION
The winter months (November to March) have the highest incidences of
combined precipitation (rain and/or snow), which occur more frequently in
winter, but average monthly Bight values indicate only slight seasonal changes
(Table A-3).
TABLE A-3. AVERAGE PRECIPITATION PER MONTH
(Nearest 1.0 inch)
Jen
3
Fcb
3
Mar
4
Apr
4
May
4
Jun
3
Jul
4
Aug
5
Sep
j
Oct.
3
Nov
4
Dec
4
Source: Modified from Lettau et al., 1976.
PHYSICAL OCEANOGRAPHY
Physical characteristics of the New York Bight are complex. Seasonal
temperature, salinity, insolation, and river runoff are complicated by
meteorological phenomena and intrusions of slope water (Bowman, 1977).
New York Bight hydrography exhibits clear seasonal cycles in temperature,
salinity, and density parameters. Two distinct oceanographic regimes, witti
short intervening transition periods prevail annually. Early winter storm
A-4
-------
mixing and rapid cooling at the surface create a well-mixed, unstratified
water column. A moderate stratification develops in early spring due to heavy
runoff from the Hudson, Raritan, and other rivers. With increasing vernal
warming, stratification changes rapidly from a saline to a thermally
maintained formation. Transition is rapid, usually occurring within one month
tCharnell and Hansen, 1974). Rapid formation of the seasonal thermocline
divides the water column into upper and lower layers. Bottom waters retain
specific characteristics with little modification until storms break up the
thermocline in the late autumn.
Familiarity with physical characteristics of New York Bight helps to
understand waste disposal since these factors determine immediate dilution and
dispersion of wastes and the transposition of contaminants. Excellent sources
for physical oceanographic patterns in the Bight are Hanson (.1977) and Hardy
et al. (1976).
WATER TYPES
Three water types have been identified in the New York Bight shell waters
by Hoilman (1971): (1) Inlet Water (hereafter called Hudson River Plume
Water, after Bowman and Wunderlich, 1977), (2) Surface Shelf Water, and (3)
Bottom Shelf Water.
HUDSON RIVER PLUME WATER
The combined discharge of the Hudson and Raritan rivers flows from the
Lower Bay into the northwest corner of the Bight Apex as a low-salinity plume,
less dense than the Shelf Waters. Consequently, Hudson River Plume Water
floats over the Shelf Waters in the Bight. Discharge volumes are maximal in
April and minimal in August. Approximately half the annual discharge occurs
during March, April, and May (Bowman and Wunderlich, 1976). This river flow
lasts as a plume all year, the extent and depth being highly dependent on flow
rates in the Hudson and Raritan Rivers (McLaughlin et ai., 1975). Generally ;
the plume flows southward between the New Jersey coastline and the axis of the
Hudson Shelf Valley. During the winter, however, the plume may flow eastward
A-5
-------
between the southern coast of Long Island and the axis of the Hudson Shelf
Valley or, in some instances, the plume may split and flow both eastward and
southward.
SURFACE SHELF WATER
With the onset of heavy river discharge in the spring, surface salinities
in the Bight decrease and a moderate saline-maintained stratification occurs,
separating Surface Shelf Water from Bottom Shelf Water. Decreasing winds and
increasing insolation, however, cause a stronger thermccline to develop
(Charnell and Hansen, 1974). This two-layer system reaches its maximum
strength by August. Surface Shelf Water is characterized by moderate salinity
and high temperature.
BOTTOM SHELF WATER
During winter, the water is essentially homogeneous over the Bight Shelf.
With the rapid formation of the thermocline and separation of Surface Shelf
Water in the spring, bottom waters become isolated until the next winter.
Bigelow (1933) found that this "cool pool" (temperatures typically less than
4"C) extended from south of Long Island to the opening of Chesapeake Bay.
This cold water persists even after the surface layers have reached the summer
maximum. Bigelow (1933) also found that the cool pool was surrounded on all
sides by wanner water. The upper layer of the Bottom Shelf Water is usually
found between 30 and 100 m during the summer (Bowman and Wunderlich, 1977).
Seaward, near the Shelf edge, steep temperature, salinity, and density
gradients prevent large-scale mixing from occurring between Shelf and Slope
Waters.
CURRENT REGIMES
Currents in the New York Bight are characterized by large temporal vari-
ability, which makes it impossible to resolve the "average" current patterns.
This great variability results from several competing influences (namely,
tidal currents, estuarine and Shelf valley circulation, and local wind
effects). The currents may be so random that only their statistical effects,
not their organized patterns, can be predicted (Hansen, 1977).
A-6
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TIDAL CURRENTS
The flow of the tidal current in the middle-Shelf region of the New York
Bight is anticyclonic (clockwise). Velocities decrease offshore and the tidal
ellipse is on a northwest/southeast axis. Tidal currents are important in the
initial distribution (mixing and dispersion) of dumped materials on the
bottom. They may also resuspend settled solids. Although bottom tidal
current velocities are low, about 10 cm/sec, coupled with wind-driven currents
during storms, they can resuspend and subsequently redistribute sediments.
SURFACE CURRENTS
The synergistic effects of temperature, salinity, river runoff, prevailing
winds, and tides produce complex and variable circulation patterns within the
bight (Hardy et al. , 1976). Seaward of the 100-m contour, geostrophic drift
induces westerly to southwesterly currents having an average speed of 10
cm/sec. Within the 100-m isobath, surface currents are hignly variable and
strongly influenced by winds and surface runoff. Currents within 30 km of
shore still depend on winds for direction but have consistently higher
velocities than the distant offshore areas. The southerly flow of the Hudson
River plume along the coast forces an opposing northward flow of more saline
waters to the east. Consequently, the nearshore water often contains a small
anticyclonic (clockwise) gyre (Hardy et al., 1976).
In general, average surface currents inshore of the 100-m isobath (.which
includes the entire Apex) flow alongshore southward from Cape Cod to Cape
Hatteras at mean speeds of about 5 cm/sec (Bumpus, 1973), except during
periods of strong southerly winds and low runoff (Bumpus, 1969). Flows in the
outer Bight are characteristically southwest with speeds of 4 to 5 cm/sec at
the surface decreasing to 2 cm/sec, or less, closer to the bottom.
BOTTOM CURRENTS
Near the Hudson estuary, classical estuarine circulation occurs with
low-salinity surface water flowing offshore and more saline water flowing
A-7
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onshore along the bottom. Hansen (1977) reports that average shoreward
current speeds as great as 5 cm/sec have been observed in the Hudson Shelf
Valley over periods as long as a month. Bumpus (1973), summarizing 10 years
of sea-bed drifter returns, has inferred that onshore Bottom Shelf current
speeds average 0.9 to 1.3 cm/sec.
The axis of the Hudson Canyon separates the general bottom currents. East
of the canyon, flow is westerly; west of the canyon, flow is northerly. This
cooler, more saline bottom water, may reach the Hudson River estuary,
dependent upon the season and amount of surface runoff; bottom water may reach
the surface during periods of southwesterly winds which cause upwelling south
of Long Island (Hardy et al., 1976).
TEMPERATURE DISTRIBUTION
Water temperatures in the Bight follow well-defined seasonal cycles.
Surface waters usually reach a minimum (2°C) in January when strong vertical
mixing and low river runoff create a vertically homogeneous water mass. In
April, the surface waters begin to warm with a thermocline developing during
the late spring and early summer. The thermocline is strongest in the late
summer, with surface temperatures peaking (24°C to 26°C) in early August. The
thermocline begins to decay with normal cooling and by late October, the
isothermal layer is 20 m thick. By mid-November further cooling and winter
storms produce an almost homogenous water mass within the 80-m contour
(Bowman, 1972 and 1977) .
SALINITY DISTRIBUTION
The salinity cycle is more complex than the temperature cycle because of
three factors which influence salinity: (1) the influx of river runoff, (2)
evaporation minus precipitation, and (3) the advection and mixing of more
saline Slope Water (Bowman, 1977). Maximum salinities (33 to 34 ppt) are
found inshore during the winter (February and March) when subfreezing
conditions reduce river runoff. River runoff during the spring thaw reduces
the surface salinity and strong vertical gradients may develop. In summer,
surface salinities are at their minimum (27 to 31 ppt) and bottom salinities
A-8
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are 27 to 29 ppt. In the late summer, when the fresh water input decreases,
salinities begin to increase towards their winter maximum ^Bowman ana
Wunderlich, 1977).
WAVES AND WINDS
SURFACE WAVES AND WINDS
Waves are beneficial in diluting and dispersing the waste more rapidly
until they become too high and restrict disposal operations. Figure A-l shows
the distribution of the percentage frequency of waves greater than or equal to
1.5 m (solid lines) and greater than or equal to 3.7 m (dashed lines) for the
mid-Atlantic Bight. Wave energies are greater in winter. The contours
parallel the coast and most of the higher frequencies seaward. Wave
directions parallel the wind patterns over the northeast United States. There
is a distinct reversal in the prevailing wind pattern between summer and
winter. During the summer (May through August) wind and waves derive most
frequently from the southwest. In the winter (September through April), wind
and waves are most frequently from the northwest.
Wave heights greater than 6.1 m occur about 2% of the time in the winter
months of December, January, and February. The median significant wave height
for this region is about 1.2 m in winter and about 0.6 m in summer. The
Middle Atlantic Bight is generally not subject to unusually high waves (U.S.
Naval Weather Service Command, 1970).
INTERNAL WAVES
Internal waves on the Continental Shelf and in the Hudson Shelf Valley have
been identified in satellite imagery studies (Apel et al., 1974). Stratified
water conditions must be present for the generation of internal waves which
can contribute to sediment resuspension and must be considered in evaluating
bottom sediment transport.
A-9
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31 2 FT.
Figure A-l. Frequency of Waves on a Percentage Basis
from Month to Month (Bumpus et al., 1973)
A-10
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GEOLOGY
The New York Bight extends 430 nmi (800 km) from Cape May, New Jersey to
Montauk Point, Long Island. Offshore New York City, the Continental Shelf
extends 100 nmi (130 km) seaward, and a series of Shelf valley complexes has
formed because of the postglacial sea-level rise (Swift et al. , 1976). The
Bight Apex is north of 40°10'N (Shark River, New Jersey) and west of 73°30'W
(Jones Beach, Long Island).
The most common sediments in the Bight are fine to medium sands. Isolated
patches of coarse sand and gravel occur near the Long Island and New Jersey
shores. The Continental Shelf contains numerous ridges and troughs which
resemble remnant barrier islands. The Hudson Channel, a relict submarine
canyon, transverses the shelf and extends from the mouth of New York Harbor
south to the head of Hudson Canyon. The Hudson Canyon runs in a southeast
direction, to the edge of the Shelf (Williams, 1974). Stubblefield et al,
(1977-) reported that the sediments in the Bight are in textural equilibrium in
the existing hydraulic climate. Silts and muds may accumulate only below
depths,of 24 m.
BATHYMETRY
Ttie well-defined Shelf valley complexes, which are narrow or broad shallow
depressions, are scoured by currents and often terminate in delta-like
terraces. Sand transported by littoral drift from nearby coasts frequently
forms sills across valley heads. More extensive sand banks (called sand
massifs) form on seaward shoals near estuary mouths (Figure A~2). The
morphology of the Delaware, Great Egg, Hudson, and Block Shelf Valleys in the
Bight follows this pattern (Swift et al., 1976).
Plateau-like expanses (stretching between Shelf valleys) vary from nearly
flat plains to patterns of undulating sand ridges reaching 10 m high and 2 to
4 km apart. The ridges appear highest on the northeastern sides of the shoal
massifs. This sand ridge and swale topography is characteristic of the
mid-Atlantic Bight.
A-ll
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>
I
76° W
74°W
••• SURFACE CHANNEL
• ••• SUBSURFACE CHANNEL
, SCARP
SHOAL RETREAT MASSIFS
200m-
CUESTAS
SHELF EDGE, MID-SHELF DELTAS
SAND RIDGES x
Figure A—2. Morphologic Framework of the New York—New Jersey Shelf
{Modified from Swift et al., 1972}
-------
SEDIMENT TYPES
Clean sand facies occur in the Inner and Middle Snelf, and muddy sand
facies on the Outer Shelf (McKinney and Friedman, 1970). Occasionally,
remnants oi the mud facies on the Middle Shelf are found embedded in shell
fragments buried in the clean sand, indicating that the muds were deposited
prior to the clean sanu (Biscaye and Olsen, 1976).
The Shelf off New York is covered by sand-sized particles with isolated
gravel patches (.Schlee, 1973, 1975). Silt dominates seaward of the 60-m
isobath and in the Hudson Shelf Valley. Silt is also present in lagoons and
estuaries with only light wave activity. Small mud patches, often seasonal in
nature, occur in the nearshore areas of Long Island to the west of Fire
Island.
Sediment types have been mapped in the Apex of the Bight (Freeland et al.,
1976) (Figure A-3). The topographically low Hudson Shelf Valley and the
Christiaensen Basin contain fine-grained sediments; the other areas contain
variously sized sands and both artifact and natural gravel deposits. The most
common sediments are silty fine sand and slightly gravelly fine to medium sand
(Harris, 1976).
SUSPENDED PARTICIPATE MATTER
The sizes of inorganic particles in the Bight Apex are similar to fine silt
or clay. Suspended fluvial sediments discharged onto the Shelf are composed
of 85% inorganic and 15% combustible organic materials (Hathaway, 1971). The
inorganic constituents are carried from the Hudson River. The organic
combustibles are from anthropogenic sources and are introduced via river
outflow, surface runoff, atmospheric fallout, and ocean disposal. In general,
particulate concentrations decrease with distance from the shore, especially
in surface waters. Vertical mixing of suspended particles, however, is
limited by the seasonal thermocline (Biscaye and Olsen, 1976).
Only about 10% of the riverborne suspended solids reach the coastal waters,
and the solids are carried in the less saline, surface layer plume. Some SPM
A-13
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40°30'N|—
40°20'N
74°00'W
CONTOUR INTERVAL: 5fm
= MUD
| | SILTY-FINE SANDS
73°50'W
73°40'W
| | FINE-MED. SANDS IvX SANDY GRAVEL
III! COARSE SANDS 'fgjg ARTIFACT GRAVEL
Figure A-3. Distribution of Surficial Sediment Based on
Visual Sample Examination. Bathymetry from 1936 Data.
(Freeland et al., 1976)
is carried back into the Lower Bay by the onshore bottom flow (Meade et al.,
1975). The resuspension of fine, inorganic sediments near estuary mouths is
related to the effects of wave surge and wind-drift currents in these shallow
waters. Drake (1974) estimates that a single November storm resuspended
10,000 tonnes of fine sediments throughout the water column in the Bight Apex,
indicating the great influence of storms in sediment resuspension.
A-14
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GRAIN SIZE
Medium-coarse sands predominate on the inner and middle Shelf, whereas
silts are the major components of the Outer Shelf. Inner Shelf sediments off
Long Island are of uniform size (.well sorted;, while Middle and Outer Shelf
areas are more poorly sorted. This indicates that sediments on the Inner
Shelf have undergone more mixing and transport than sediments in deeper water.
SCubblefield et al. (1977) identified two sand provinces in the Bight: the
New Jersey Platform sand province and the Cholera Bank sand province, where
medium-grain sands predominate. Finer and coarser sands stretch out in a
north- to northwest-trending band off New Jersey while the Cholera Bank sands
are more homogeneous.
The topographic highs surrounding Christiaensen Basin are covered by a
medium-grain sand, while towards New Jersey, sand ribbon patterns with 10- to
200-m spacing appear. Stubblefield et al. (1977) report that mud facies occur
only in the tributary channel of Christiaensen Basin and on the western side.
They also reported that the basin floor deposits become coarser toward shallow
water.
TRANSPORT
Sediment transport is produced by two basic phenomena: tidal flow which
stores sand in estuary mouths, and storm wave action which moves sand between
estuary mouths. Sand discharges from surf zones off the Long Island and New
Jersey coasts move towards the New York harbor mouth and have built Sandy Hook
and Rockaway spits (Swift et al., 1976).
On the Snelf proper, westward and eastward currents measured from bottom,
mid-depth, and surface locations showed that surface flows have an offshore
component in both east and west directions (Lavelle et al., in press).
However, with increasing depth, the westward bottom flows begin to parallel
isobaths and the eastern flows tend to move shoreward. The result is a net
southwest migration of sand particles along the bottom.
A-15
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Lavelle et al. (1975) concluded that transport occurred during brief,
intense transport events separated by vast periods of quiescence. As a
function of excess velocity, more efficient transport occurs during intense
rather than mild storms. The potential consequences are that if bottom
currents in any of the dump sites exceed the threshold velocity and overcome
the fractional components of the waste material (e.g., during storms), ttie
dumpsite may be scoured clean of waste. This sequence may have occurred in
the Sewage Sludge Site, where only traces of sewage sludge can be found.
Harris (1976) reported that substrate mobility is greatest near Long Island
and northern Christiaensen Basin and varies seasonally. Kuc dominates in Luc
late sprn.t. trie early summer and may even cross intuivciung sanci-vrve crests.
Trougii areas are mud-free in early f^ll until eerly spring because oi bottom
current scour. The mud facies moved to within 5.0 km of Long Island between
winter and summer, but later moved back to 9.3 km from Long Island. The
distribution of muds are very important in evaluating the effects of waste
disposal since trace metals and other waste constituents are present in higher
concentrations in muds than in sands.
CHEMICAL OCEANOGRAPHY
The New York Bight receives wastes from a large metropolitan area. The
sources of these wastes include ocean disposal, sewage outfalls, river
discharge, groundwater seepage, land runoff, petrochemical processes, and
atmospheric fallout.
It is difficult to determine effects of any particular type of waste
disposal since contaminant sources are so varied and inputs are large.
Contaminants may be changed from one chemical state to another by synergistic
interactions with seawater, biologically assisted changes, or oceanographic
events which affect mixing and sediment turnover (MESA, 1974).
This section covers the spatial and temporal variability in the water
column, sediments, and biota relevant to the wastes presently released at the
Acid Site. References are made to various sources for those parameters (e.g.,
A-16
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nutrients) unaffected by acid waste disposal. Sufficient chemical data are
available for site designation and future decision-making for wastes released
at the site.
Excellent overview sources for chemical features of the Bight are Alexander
and Alexander (1977) and Segar and Cantillo (1976; .
WATER COLUMN
DISSOLVED OXYGEN
Dissolved oxygen concentrations in the surface waters of the Bight are
greater than or equal to the saturation level (Corwin, 1970). At a 20-m depth
(66 ft) in the Apex, the percentage of saturation in control areas located
outside the disposal sites was 55% to 90%.
In contrast, at 20-m depth near the edge of the Sewage Sludge Site, the
oxygen concentration was 1.6 mg/1 (26% saturation), and at the center of the
site the saturation was 10% (Pearce, 1969). It is not known if this oxygen
depression was due to sewage sludge disposal.
Subsurface oxygen concentrations may vary seasonally (Corwin, 1970). Below
10 m (33 ft), concentrations are lower in September than in November, due to
stratification of the water column in the summer and higher biological and
chemical oxygen demands. In April, oxygen concentrations usually approach
saturation.
Garside and Malone (1978) suggest that the near-surface variation in
dissolved oxygen is not significantly above zero. Oxygen production from
photosynthesis in the Apex is sufficient to balance organism respiration or
the degradation of organic material and anthropogenic sources from naturally
occurring. With respect to total carbon respired in the Apex, 77% is derived
from naturally occurring sources, sewage sludge contributes another 7%,
surface runoff 7%, and the Hudson Estuary about 9% (Garside and Malone, 1978).
Since the Apex-derived carbon supply is about three times greater than all
other external carbon sources, normal oxygen production has been adequate to
A-17
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balance the respiration demands of the system. Local anoxic conditions, which
occurred in sorre deep Bight areas during the summer of 1976, are only likely
below the thermocline, when the surface (oxygenated) and subsurface (oxygen
depleted) waters do not mix.
PH
The pH of Bight waters ranges from 7.6 to 8.4; surface values are usually
higher than bottom values because of the dynamic relationship with atmospheric
C0? at the surface (which increases alkalinity) and the decomposition of
organic material (which increases acidity) in subsurface waters (Alexander and
Alexander, 1977).
Seawater is an extremely well-buffered solution. Changes in pH are
temporary and usually the pH returns to normal ambient values almost;
immediately after it is perturbed (Duxbury, 1971) (Appendix B).
TRACE METALS
The effects of trace metals in the water column are determined by the
concentrations, chemical species, and availability to the biota. Certain
metals may stimulate or depress biological activity or may become concentrated
in the food chain (Alexander et al., 1974). Segar (1975) noted large temporal
and geographic variations of trace metal concentrations in the Bight, caused
by river discharges, ocean waste disposal, or complex oceanographic and
meteorological events. Normal levels of trace metals in unpolluted seawater
samples are listed in Table A-4.
Two conclusions can be drawn from these data. The values for metal concen-
trations in the Bight are higher than in uncontaminated sea water samples,
but, apart from manganese, the ocean disposal sites do not raise actual levels
in the overlying water.
These data (Table A-4) can be compared to trace metal levels in the Apex
and offshore control sites (Segar and Cantillo, 1976; Table A-5). The area of
disposal influence indicated in Table A-3 refers to all potential sources of
contamination (acid waste, dredged material, sewage sludge, and cellar dirt).
A-18
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TABLE A-4. MEAN TRACE METAL LEVELS IN UNPOLLUTED SEAWATER SAMPLES
(1)
(2)
(3)
yg/ liter (ppb)
Cadmium
0.1
—
0.1
Chromium
0.05
—
0.05
Copper
3
3
3
Iron
10
10
6
Mercury
0.03
—
—
Manganese
-
2
2
Nickel
500
--
—
Lead
0.03
—
0.03
Zinc
10
10
lu
Source: (1) Goldberg, 1963; (2) Riley and Skirnow, 1965;
(3) Buelow et al., 1968) .
TABLE A-5. MEAN TRACE METAL CONCENTRATIONS IN THE NEW YORK BIGHT
(Standard Deviation) yg/1 (ppb)
Metal
Surface
Disposal
Sites'
Influence
Control
10 Meters
Disposal
Sites'
Influence
Control
Cadmium
0.6 tO. 42)
0.8 (0.40)
0.6 (0.28)
0.5 (0.19)
Copper
4.3 (1.98)
4.6 (1.62)
4.7 (1.60)
4.0 (2.08)
Iron
15.3 (8.38)
18.6 (16.5)
16.4 (9.88)
17.1 (8.09)
Manganese
5.3 (1.38)
3.7 (1.50)
9.6 (5.19)
4.7 (1.70)
Zinc
32.5 (8.66)
35.0 (12.25)
32.5 (13.23^
30.0 (10.80)
Source: Modified from Segar and Cantillo, 1976. Means are for 7 months
between May 1974 and March 1975.
NUTRIENTS
Acid wastes do not contain significant levels of the elements required for
phytoplankton growth (Appendix D, Table D-2). Consequently, the disposal of
acid waste does not markedly affect the distribution or concentration of
nutrients in the water column. Therefore, seasonal and spatial variabilities
of the nutrients are not discussed in this EIS. The interested reader is
referred to Corwin (1970), or Alexander and Alexander (1975 and 1977) for
discussions of nutrients, and to Mueller et al. (1976) for discussions of the
sources and mass loads of nutrients from anthropogenic sources into the Bight.
A-19
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ORGANIC COMPOUNDS
Acid waste does not contain significant amounts of organic compounds.
Disposal operations, however, may affect the phytoplankton in the barge's
wake. Chlorophyll a concentrations in seawater can be used as indicators of
phytoplankton abundance, thus changes in concentrations can be used to
interpret micronutrient fluctuations. In general, chlorophyll & concen-
trations are greater in the upper water column because of increased produc-
tivity in the euphotic zone and, particularly in the Apex, because of large
nutrient inputs. An increase in surface water concentrations of chlorophyll £
from 0.5 to 8.0 yg/1 in September 1969, to greater than 4.0 to 8.0 yg/1 in
April 1970, was associated with a spring plankton bloom (Hardy, 1974).
Corwin (1970) and McCarthy (1970) have additional information about parti-
culate carbon and organic nitrogen in the Bight.
SEDIMENTS
TRACE METALS
Elevated concentrations of iron, manganese, titanium, copper, tin,
chromium, zinc, lead, and nickel have been measured in many areas of the New
York Bight (Biscaye and Olsen, 1976; Pearce et al., 1977). Iron and magnesium
are common throughout the Bight; the other metals are more common in sediments
near the Sewage Sludge and Dredged Material Disposal Sites and in areas of
river discharge.
Grieg et al. (1974) investigated trace metal concentrations in the Bight
Apex and concluded that there were insignificant seasonal variations in the
levels of copper, chromium, lead, nickel, and zinc, except near the Dredged
Material Site. Elevated sediment concentrations were not observed near the
Acid Site. Decreases in trace metal concentrations away from the center of
disposal sites, and areas of elevated concentrations to the northeast of the
sites and in the Hudson Shelf Valley, imply dispersal of wastes by water
currents (Carmody et al., 1973).
4-20
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ORGANIC CARBON
Acid waste contains no significant amounts of organic carbon, nor does it
affect the distribution of organic carbon in the Apex. The total organic
carbon (TOG) content of sediments is important since sediments with different
levels of TOC may support different biotic communities. Trace metals are more
abundant in sediments which have a high TOC content. Harris (1976) and
Hatcher and Keister (1976) dis'cuss TOC in New York Bight sediments.
CHLORINATED HYDROCARBONS
Persistence and toxicity of chlorinated hydrocarbons, e.g., DDT (dichloro-
diphenyltrichloroethane) and PCB (polychlorinated bi-phenyl), cause great
concern about their abundance and distribution in marine environments.
However, acid waste does not contain chlorinated hydrocarbons (ERGO, 1978a,b).
West et al. (1976) have information about the distribution of PCB1 s and DDT
near the Dredged Material and Sewage Sludge Sites.
BIOTA
TRACE METALS IN ZOOPLANKTON
Extensive species lists and zooplankton abundance measurements, including
studies by Grice and Hart (1962), Jeffries and Johnson (1973), Falk et al.
(1974) and Gibson (1973) exist for the New York Bight. Several species of
Apex zooplankton were examined for trace metal contaminants. Levels of copper
and lead varied among species examined, and zinc varied according to the
location of the sample. It has not been possible to determine the source of
the contaminants (Greig et al., 1977). At the Delaware Bay Acid Waste Site
(where the waste characteristics are similar to those at the Apex Acid Site),
Johnson and Lear (1974) reported extreme variability in the concentrations of
trace metals in the zooplankton, probably due to the complex nature of
contaminant inputs and the dispersal of planktonic organisms by water column
movement and mixing.
A-21
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Contaminants which accumulate in the eggs and in developing larvae of
marine fauna can cause chromosomal mutagenesis at subtoxic levels (Longwell
1976; Westerhagen et al., 1974). Longwell (1976) determined that there was a
significant increase in the number of chromosomal aberrations in eggs and
larvae of the Atlantic mackerel, Scomber scombrus, near the Acid Site. Away
from the dumpsite in the general area of the apex, a lower percentage of
abnormalities was observed.
TRACE METALS IN BENTHIC BIOTA '
Levels of trace metals in benthic macrofauna of New York Bight are reported
in NMFS (1972), Pratt (1973), and Pararas-Carayannis (1973). Sedentary
benthic organisms are the preferred indicators of the effects of environmental
contamination, because they are directly exposed to sediment-bound trace
metals and unable to move from stressed areas (Pararas Carayannis, 1973).
NMFS (1972) reported that some specimens contained levels of lead, chromium,
and mercury above the normal range of values for the animals. These animals
were in the vicinity of the Dredged Material and Sewage Sludge Sites.
Vaccaro et al. (1972) measured elevated trace metal concentrations in some
benthic animals collected from New York Bight Acid Waste Disposal Site.
Elevated concentrations of iron were detected, but no documented lethal or
chronic effects exist for the epifauna and macroinfauna at the Acid Site.
Earlier work by RedfieH and Walford (1951) and Westman (1958) led to the same
conclusion.
Pearce et al. (1976d) noted that disposal areas, characterized by large
heavy metal and/or organic concentrations, showed a decline in the number of
benthic individuals from 1973 to 1974; however, the species composition did
not vary significantly during the same period. They concluded that the Bight
biota are reasonably dynamic in abundance, and that correlations of abundance
to trace metal concentrations must be made with caution.
BIOLOGICAL CHARACTERISTICS
The biota in the New York Bight demonstrate complex diurnal, seasonal, and
longer-term cycles of species composition and abundance. Several factors
A-22
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contribute to these cycles: the influence of various wafer masses, each with
its characteristic biota, the location of ph,e Bight;, between the boreal fauna
(found to the north) and the temperate to subtrppical fauna (found to the
south), the effects of upusual or a period^ physical conditions, and the
varying locations and amounts of anthropogenic input,
The Bight is biologically heterogeneous , T^is section, however, only
discusses those environmental aspect? p£ the reg>pn which are directly
relevant to the specific conditions at the Acid S^te, The water is described
first, then the benthic biota are characterised. Fpr< the benthos, organisms
characteristic of a sandy bottom are treated in Ifhe mp?t detail. Since the
bottom type at the Acid, Site is medium to fine sqnd, the biota typical of
other sediment types (muds, canyon slopes, rOpky outcrops, artificial
structures, or coarse sa^nd and gravel) ^n thfif Bight are not: pertinent to this
EIS. Appendix B describes the environmental characteristics and biota of the
site proper.
WATER COLUMN
The dynamics of the water and its biofa affect the entire Apex. The
plankton (microscopic plants and animals moving passively with the water) have
patchy distributions in space and tijne, Quantities of individual species vary
seasonally; different species may ^be abundant in .successive years, and species
composition is not predictable;. Physical and chemical parameters which
influence plankton are known, but because {the seasonal changes in species
cannot be reliably predicted, it ^ diffipult to determine why a species is
present or absent in an area. (Consequently, individual species are poor
indicators of pollution. Since the plankton mpye with the water throughout
the Bight, it would be extremely difficult, if not impossible, to relate
long-term changes in the populations to any specific disposal site or other
pollutant source.
The nekton contain several species of CPtnmerqia,lly or recreationally
important fish. As wil^h the plankton, the mobility of the fish makes it
difficult to demonstrate that changes in the population dynamics are related
to a specific dump site or pollutant source. flpwever, fish have been
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extensively surveyed and are economically important, Fish are the most direct
link with man, via the food chains to toxic contaminants in the acid waste.
MICROBIOTA
The waste released at the Acid Site does not contain pathogenic organisms,
nor does the disposal of acid-iron waste significantly affect the distribution
and abundance of the microfauna in the Bight.
PHYTOPLANKTON
Phytoplankton in the New York Bight have been extensively investigated for
the past 75 years. Work has concentrated on the seasonal changes and the
major physical and biochemical factors controlling primary production in the
Bight. The information in this section is taken from monographs by Malone
(1977) and Yentsch (1977). Additional informatipn, including species lists,
can be found in Barber and Krieger (1970), Esaias (1976), Falkowski and Howe
(1976), Freudenthal and Lee (1963), Hulburt (1963), Martin (1928, 1929a,b),
Riley (1952), Ryther (1954), and Smayda (1973). Table A-6 shows the more
abundant species in the Bight.
TABLE A-6. PHYTOPLANKTON SPECIES WITH CELL DENSITIES
GREATER THAN TEN THOUSAND PER LITER IN THE NEW YORK BIGHT
Species
Skeletonema costatum
Thalassionema nitzschioides
Rhizosolenia alata
Asterionella japonica
Rhizosolenia delicatula
Rhizosolenia alata
Chaetoceros socialis
Calycomonas gracilis
Month
Dec
Dec
Dec
Feb
Feb
Sept
Mar
Apr
Max itnum
Observed
Density
x 10,000
50 to 60
7
2
10
2
1
10 to 90
9
After Hulburt 1963, 1966, 1970; Hulburt and Rodman, 1963
A-24
-------
Phytoplankton in the New York Bight Apex have strong similarities to those
found in estuarine and bay water s^ The ohlorpplyte, Nannochloris atomus,
and the dinoflagellate , Ceratium tripos, (Dominate the phytoplankton assemblage
from the late spring until middle to late summer^ Diatoms dominate during the
colder autumn and winter months, S ke 1 e t pnema Q o s tat urn , Thalassiosira spp. and
Leptocylindrus danicus ar? frequently, although not always, the dominant
species .
Although they cannot be used as indicators of water quality, some phyto-
plankton species do reflect man's influence qr> the Bight, According to Smayda
(1973), Nannochloris atomus is an indicator pf eutrophication. Excessive
population growth of Ceratium or Nannpchlpris has caused oxygen depletion in
bottom waters, besides reducing the populations of more desirable phyto-
plankton food species fop pys,ters and elsiqs. Oxygen depletion of the bottom
waters and associated fish kills had been reported earlier (.Smayda, 1973), yet
the most extensive oxygen Depletion and benthic mortality occurred in the late
summer of 1976. Apparently, unusual meteorological events, a large population
of Ceratium tripos t and a lack Of her^ivprpus gopplankton produced the
condition (Sharp 1976; S^teimle 1976). Barged pq«an disposal of sewage sludge
and dreaged material may havt; contributed to the event, but Segar and
Berberian (1976) stated that nitrogen input 'fjrow the rivers (.caused by waste
wster discharge) is the greatest single problem,' in the New York Bight.
ZOOPLANKTON
The distribution and abundance of zppplanktpn populations in the Apex of
the Bight have been extensively studied for many years , The material in this
section is primarily from the, monographs by flalpne (1977) and Yentsch (1977).
Further information and data are, found in Austin and Dickinson (1973), Bigelow
and Sears (1939), Deevey (1956), Qrice and Hart (1962), Herman et al. (1968),
Jeffries and Johnson (1973), and Sandy Hook Labpratory (1972). Table A- 7
lists species fpr the major seasons in the
Unlike phytoplankton, the zooplankton in the Apex have strong similarities
to those found offshpre in the outer Bight. Copepods (Oithona similis,
Paracalanus parvus, , Pseudocalanus roinutus , Temora longicprnis , and Centropages
A-25
-------
typicus) dominate the population throughout the year. Warm water oceanic-
species are often present during the summer and autumn mouths, but have not
been reported in the Hudson estuary.
Seasonal peaks in abundance are usually bimodal with the highest numbers
found in July and November (after the spring and autumnal phytoplankton
blooms). Cropping by herbivorous zooplankton reduces the size ol the summer
phytoplankton population. Zooplankton densities are lowest during the winter
months; the decline from the fall peak is accompanied by a rise in the numbers
of carnivorous ctenophores.
Zooplankton are important biological components in assessing the impact of
man's activities in the Bight. They may concentrate contaminants from the
phytoplankton or the water and many fish feed directly upon zooplankton. This
feeding provides a direct link with such contaminants to humans. Grey et al.
11977), determined the levels of several trace metals in the zooplankton in
the Bight, but could not determine any differences in metal.levels which were
related to the geographical locations of sampling.
NEKTON
Many finfish of commercial and recreational importance are found in the New
York Bight. Their diversity and abundance is due to the geographical location
of the Bight which is the northern limit of temperate and subtropical migrants
and the southern limit of boreal migrants. Some species are found inshore,
others offshore, and some migrate from inshore to offshore. Significant
numbers of adults, planktonic eggs, and larvae can be found over the entire
mid-Atlantic Shelf throughout the year. Consequently, waste disposal activity
in any area of the Shelf carries a potential risk of adversely affecting the
fish (Grosslein, 1976) .
Numerous surveys of pelagic and demersal fish have been made (Table B-i).
However, because of the large area these surveys cover (usually Cape Cod to
Cape Hatteras) , the number of stations is limited, so the precision of each
survey is low and only major changes in the fish populations are detectable.
A-2 6
-------
TABLE A-7. SEASONAL OCCURRENCE OF ZOOPLANKTON IN THE NEW YORK BIGHT APEX
Species
HOLOPLANKTON
Cope.poda
Oithona s,imij.is
Paracalanus parvus
Parac^aianus cirassirostris
Pseudocalanus minutus
Centrppages hamatus
Centrppages typigus
Tetnora longicornis
TortanVis discaudatus
Ac-artia clauei '
Acartia tonga
Labidocera aestiva
Corycaeus
, Calanus f inmarchicus
guryjeinpra '
Canadia
Eucslanus
Metridia
Rhincalanus
Clytemn,estra
Cladoce'ra
Podory
Evadne
Penilia
Siphonophpra
Ctenophpra
Mysidaeea
Am phi pods
Gamsriaae
Hyperidae
Tynicata
Thfllacgn
Oi,kop,|euira
Polychaet^a
Tomapteridae
N^tnatoda
Ectoprocta
Chartoyn^tha
MgRGPLANKTON
Polycfiaeta
Gastropoaa
Bivalve
Barnaqle
Decapoda
Pnoroniqa
Echinodermet^
Fisn larvap
Fish eggs
Season
Winter
A
A
A
A
A
A
A
B
B
B
B
B
B
'B
-
-
-
-
B
.-
A
-
,B
-
B
-r
-
-
B
B
-
B
A
A
A
A
B
B
-
-
-
B
Spring
A
A
A
A
A
A
A
A
A
A
A
B
A
B
-
-
B
-
B
-
A
-
A
-
-
-
-
-
B
-
B
A
A
A
A
A
B
B
B
B
B
A
Summer
A
A
A
A
A
A
A
A
A
A
-
-
A
B
-
-
-
-
B
A
A
A
A
B
B
-
B
B
B
A
A
A
A
B
A
B
B
B
A
Autumn
A
A
A
A
A
A
A
B
A
A
A
A
A
-
-
B
B
B
B
B
A
A
A
B
B
B
B
A
A
-*
B
A
A
A
A
A
B
A
B
A
B
B
- * No occurrence
A a Presenf at 50*. or more of stations sampled
B = Present at less than 50% of stations sampled
Source: After Gibson 1973
A-27
-------
In the Bight Apex, the finfish are potentially affected by the widespread and
varying inputs of contaminants; consequently, relating even major changes in
the fish populations to a specific source is very difficult.
The broad distribution and migration patterns of two important sport fish -
bluefish and Atlantic mackerel, are known. The National Marine Fisheries
Service has three categories for the North Atlantic Fishery Resources: based
on the importance to man, bluefish are in the high category, while mackerel
are in the medium category (Gusey, 1976). Whiting, which are fished
commercially near the site, are in the low category. The first two species
are occasionally abundant at the Acid Site.
Bluefish
The bluefish (Pomatomus saltatrix) is a warm-'water fish which winters and
spawns offshore and moves inshore during the. summer months, ((Gusey, 1976),
Wide fluctuations in its abundance have been repotted since colonial times.
The bluefish is a voracious predator on other fish, and both sea temperature
and the availability of prey are important determinants of bluefish
distribution. They are much sought after as sport fish, gqd the value of
bluefish taken by sport fisherman may be a multiple of the commercial catch
(Saila and Pratt, 1973). This makes landings even mpre difficult to estimate
because the recreational fisheries in New York are largely unregulated; the
amount of the catch and the fishing effort is not known (Ginter, 1974),
Atlantic Mackerel
The Atlantic mackerel (Scomber scombrus) is a wide ranging fish with its
distribution centered in the mid-Atlantic Bight, Spawning is in the spring
and early summer, but the fish do not prefer a particular regipn, Therefore,
the location of greatest egg production can vary from year to year, depending
on the local concentrations of the fish (Bigelow and Schroeder, 1953).
Mackerel quantities fluctuate widely from year to year. The determining
factor for this fluctuation appears to be the comparative success of
reproduction, but little is known about the factors which prompte the
A-28
-------
production and survival of larvae (Saila and Pratt, 1973). Young mackerel
have higher survival rates when there are few adults and higher mortality when
the adults are abundant (Gusey, 1976).
Mackerel are not as important commercially at this time as they were in the
1940's because demand is low (McHugh, 1977). Landings are now 1 to 4 million
kilograms (2 to 8.9 million Ibs) against the peak harvest of 33.5 million
kilograms (74 million Ibs) in 1944 (Gusey, 1976). Mackerel are still an
important sport fish, but,-as with bluefish, the recreational value of the
catch cannot be estimated.
BENTHOS
Benthos includes marine species which burrow into bottom sediments, species
attached to the bottom, and species which live and move about on the bottom.
Due to their ubiquitous nature, limited mobility, and comparatively long
lifespan, benthic organisms are frequently used as indicators of water and
sediment quality. They are often sources of food for fish and man.
Shellfish are not treated here, since the the Acid Site environs do not
have commercially or recreationally important numbers of surf clams, ocean
quahogs, or sqa scallops. The site is next to the area closed to shellfishing
(Figure A-4). Lobsters are taken northeast of the site. However, as snown in
Appendix B, acid waste 4°es not measurably affect the bottom.
The Bight Apex benthos is composed of several different communities. Pratt
(1973) recognizes three level-bottom faunal groups widespread on the
mid-Atlantic Continental Shelf: sand, silty sand, and silt-clay fauna (Figure
A-5). Since Bight Apex sediments range from sandy gravel to mud (Freeland et
al., 1976), elements of all three biotic communities can be, and are, within
the Bight. The following discussion concentrates on sand fauna, the dominant
community in the Bight Apex, which is found at the Acid Site. Table A~8 lists
the species and feeding types characteristic of the sand-bottom fauna.
A-29
-------
LONG ISLAND SOUND ^
LONG ISLAND ., .,.
1. DREDGED MATERIAL
2. CELLAR DIRT
3. SEWAGE SLUDGE
4. ACID WASTES
5. SEWAGE SLUDGE (ALTERNATE)
6. WRECKS
7. WOOD INCINERATION
CLOSED TO
SHELLFISHING
BIGHT LIMIT
DELAWARE f.
BAY
0 50
NAUTICAL MILES
38° -
Figure A-4. Area Closed to Shellfishing in the New York Bight
(FDA, 1973)
A-30
-------
LONG ISLAND SOUND ^
1. NEW YORK BIGHT ACID SITE -/
2, NORTHERN AREA
3. SOUTHERN AREA
4. 106-MILE SITE
LONG ISLAND
SANQ FAUNA
SILTY-SANP FAUNA
SILTY-CLAY FAUNA
DELAWARE f;
0 50
NAUTICAL MILES
38° -
Figure A-5. Benthic Faunal Types in the Mid-Atlantic Bight
A-31
-------
TABLE A-8. BENTHIC SPECIES CHARACTERISTIC OF
IN THE MIDDLE ATLANTIC BIGHT
SAND FAUNA
Species
Polychaetes :
Scoloplos fragilis
Nephtys bucera
Nephtys picta
Nereis arenaceodonta
Stheneiais limicola
Spiophanes bombyx
Prinospio malmgreni
Ophelia
Goniaaella
Clymenella sp.
Aricidea sp
Magelona sp.
Bivalves :
Spisula soiidissima (surf clam)
Astarte castanea
Ensis directus (razor clam)
Tellina agilis
Gastropods:
Polinices duplicatus
Lunatia heros
Amphipods :
Haustorids
Phoxocephalids
Lysianassids
Decapods :
trangon septemspinosus (shrimp)
Cancer irororatus (crab)
Ecninoderm
Echinarachnius parma (sand dollar
Ascidians
Amaroucium (sea pork)
Mogula arenata (sea squirt)
Deposit
Feeders
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
) X
rfiw» "*-7WTinT|WT
Suspension
Feeders
X
X
*
X
X
X
liii|.t)lnnfl."rn"-n, '!! " 1
Pr^d8t;or$
of
Bivalve?
x
X
^cayengers
X
X
X
X
Source: After Pratt, 1973.
A-32
-------
Sandy bottom s€jdim,ents have low organic carbon content, large grain-size,
and high mobility. Animals living on or in the ' sand are adapted to move
within the sediment and to recover from burial; the communities are usually
dominated by suspension feeders, although species with other feeding habits
can be important (Pratt, 1973). In the Bight, deposit detrital feeders and
scavengers are a^lso present. Invertebrate carnivores are rare and do not
appear to have aji important role in this community type. Demersal fish are
probably the important carnivores,
Productivity in this sediment type is usually low, although, if the surf
clam, Spisula solidissima , is present, sandy bottoms can be extremely
", '" '"V "' "
productive. Thomas et al. (1976) measured the seabed oxygen consumption over
the entire, Apex and found that the rates were comparable to other enriched
coastal areas .
The inshore benthic fauna are dominated by organisms characteristic of a
high-energy coastal environment; bivalves Tel lina agilis and Spisula
soliaissima. the sand dollar Ecninarachnjus parma , and polychaetes (e.g.,
Spiophanes bomb ax and Prinospio malmgreni) (Pearce, 1972). Benthic
" '"TV" ..... ' "^
populations in, the Bight are not static. Pearce et al. (1976a, 1976b) report
substantial annual variations in the distribution and abundance of benthic
assemblages, in the Bight Apex, when compared to earlier surveys (Pearce et
al., 197$c).
Most analytical studies of the Bight benthos investigated effects of use of
the Sewage Sludge and Dredged Material Sites. Buelow et al. (1969)
investigated the distribution of coliform bacteria in the Bight. As noted
earlier, aci«i waste does not contain bacteria. The FDA has continued to
monitor coliform bacterial levels (Verber, unpublished). Other benthos
investigators are: Frey (1973, 1974), {Jew York Ocean Science Laboratory
(1973), Pararas-qarayannis (1971, 1975), Ropes and Merrill (1976), SHL (1972; ,
and Buzas et a*,. (197?) .
A-33
-------
Rowe (1971), NMFS (1972), Pararas-Carayannis (1973), and Buzas et al.
(1972) have evaluated some of the ecological effects of the pollution of the
New York Bight. O'Connor (1975) summarized those impacts as:
• High prevalence of diseases in several species of finfish and
shellfish.
• Alterations in the distribution and abundance of bottom living
organisms.
• Widespread distribution in exceptionally high numbers of coliform
and fecal coliform bacteria indicate the presence of pathogenic
bacteria.
• Presence of bacteria which are resistant to a broad spectra of heavy
metals and antibiotics.
e Noxious concentrations of suspended particulate material, flotsam,
and surface slicks.
These effects are the result of all contaminant inputs to the Apex and most
strongly associated with three sources: outflow from New York Harbor and ocean
disposal at the Dredged Material and Sewage Sludge Sites (Appendix C).
A-34
-------
Appendix B
ENVIRONMENTAL CHARACTERISTICS OF THE
NEW YORK BIGHT ACID WASTE SITE
-------
CONTENTS
age
METEOROLOGY
PHYSICAL OCEANOGRAPHY
Water Masses
Current Regimes
GEOLOGICAL OCEANOGRAPHY ......................... 5-9
Sediment Trace Metal Contents ................... B-10
CHEMICAL CHARACTERISTICS ........................ B-12
Water Quality ....'. ...................... B-12
BIOLOGICAL CHARACTERISTICS ....................... B-15
Water Column Biota ........................ B-15
Benthic Biota ........................... B-16
Figure B-l Location of New York Bight Acid Waste Disposal Site B-2
TABLES
Table
B-l Historical Surveys in the Vicinity of the Acid Site B-3
B-2 Iron Concentration in Sediments B-14
b-3 Fish in the Vicinity of the Acid Waste Site B-l7
B-4 Comparison of Species Diversity and Abundance Values for
Acid Waste and Control Sites in the New York Bight B-18
B-i
-------
Appendix B
ENVIRONMENTAL CHARACTERISTICS OF THE
NEW YORK BIGHT ACID DISPOSAL WASTE SITE
The New York Bight Acia Waste Disposal Site was established in 194d lor the
disposal of waste generated from industries in the New Jersey area. At
present (1979;, the Acid Site is used by only two companies, NL Industries and
Allied Chemical, both located in Mew Jersey. before 1974, Uu Pont disposed of
caustic wastes from its Grasselli plant, New Jersey at the site; now, these
wastes are dumped at the 106-Mile Chemical Waste Site. The Acid Site is
10.6 nmi (.20 km; southeast of Ambrose Light, and 14.5 nmi (27 km; off the Mew
Jersey and Long Island coasts. Covering an area of 41.2 km (12 nmi ) and
located on the Continental Shelf, the site is bounded by latitudes 40°16'i\i to
40°20'N, and longitudes 73°36'w to 73°40'w. Topographically, the bottom is
almost flat, with an average depth of 25.6 m (c54 ft;, ranging from 22. o m (.74
ft; to 28.3 m (.93 ft). The site abuts the northeastern edge of the Hudson
Canyon (Figure B-l;.
Until 1947, industrial acid waste was deposited either at the Sewage Sludge
Site or in Raritan Bay. In April 194e>, a separate acid waste site covering
2 nmi was established at 40°1:>I24"N, 73°4o'42"w. In March 1949, the
dumpgrounds were moved south of 40°20'iM, and east of 73°40'w. In January
1950, seasonal dumping locations were established. The summer track was south
of 40°20'N, and east of 73°40'W. The winter track was south of 40"20'N, and
east of 73°43'W (PHSSEC, 1950;. The present site is over the summer track.
The Acid Site is only 2.75 nmi (5.1 km; southeast of the Sewage Sludge Site
and 7.9 nmi (14.6 km) trom the Dredged Material Site (Figure B-l;.
Table B-l lists the major studies which have analyzed samples from the Acid
Site. Other surveys in the Bight have encompassed the entire Apex, or
concentrated on the bewage Sludge or Dredged Material Sites. Agencies
conducting or sponsoring most of the work in this area include the NMFS
Laboratory at Sandy Hook, New Jersey, and the NOAA-MESA New York Bight
B-l
-------
73*30'
LONG ISLAND :.££'•?. :.x-
i BROOKLYN •,£. ..
LOWER
BAY
30'
20'
NEW JERSEY
10'
40°
SANDY HOOK - ROCKAWAY POINT TRANSECT
DREDGED
MATERIAL
SITE
SEWAGE SLUDGE
1
^
C
25m-
-^
ACID WASTES SITE
I
7J
I
I
I
-—^BIGHT APEX LIMITS-
\ \
•WRECK
\
WOOD INCINERATION SITE—»
\
40'
30'
20'
10'
40°
74°
50'
40'
73°30'
Figure B-l . Location of New York Bight Acid Waste Disposal Site
B-2
-------
TABLE B-l. HISTORICAL SURVEYS IN THE VICINITY OF THE ACID SITE
(Abbreviations Listed at the end of this table)
Date
sponsor/
Investigator
Purpose
Citat ion
Sept U-ld,
1976
Mar 1.3-14,
Nov
14-lu.
1977
Aug 1 3 ,
10, 16,
1977 '
Aug 1J,
Aug 12,
1977
Sept
197o
July-Sept
June
Apr 197o
i)ec
1975
Sept
1*75
Allieu Cnemical a NL
InUustries/tRCO
Allied Chemical c* NL
Industries/EGiG
Allied Chemical c* NL
Industries/EG&G
Alliea Cnemical ot NL
Industries/ EG6G
Alliea Chemical/
EG&G
NL Industries/
NOAA«/AOML
NOAA/NMFS
NOAA*/AOML
NOAA-/AOML
NOAA*/ AOML
•-
N'OAA /Raytheon
Cnemical monitoring
cruise
Cnemical monitoring
cruise
Cnemicai monitoring
cruise
Cnemical monitoring
cruise
Dispersion study of
oyproauct rlCl wastes
Dispersion stuay ot
acid-iron wastes
» a t e r c o 1 urn n
characterization
cruise""""
Investigate
the oxygen
depletion pnenomena
Water column
characterization
cruise""""
Water column
cnaracterization
for water movement
analysis
Water Column
cnaracterization
cruise""""
Baseline survey ot tne
New YorK bignt
tRCu, ly/oc
y / 7 c
y / 7 b
tlaze Iwortn ,
et ai. , ly77a
bteimle ,
unpuD 1 .
Starr et al. ,
1^77
hazeiwortn ,
ec al., i^'/'
rColitz et ai . ,
Kaycneon,
b-J
-------
TABLE B-l. (continued)
Date
Sept-Oct
1975
May- June
1975
Apr 1975
Mar 1*75
Mar 1975
Feb-Mar
1975
Jan
1975
Oct 1974
Sept-Oct
1974
Aug-Sep
1974
July-Nov
Iy74
June 1974
Sponsor/
Investigator
NOAA-/AOML
NOAA*/AOWL
iNOAA*/AOML
NOAA*/NMFS
NOAA*/NhFS
NOAA*/AOML
NOAA*/AOML
Alliea Chemical/
lnt'1. Hydronics
Corp.
NOAA*/NMFS
NOAA*/NMFS
NOAA*/AOML
EPA
Purpose
Water column
characterization
cruise**
Water column
characterization
cruise**
Water column
characterization
cruise**
Obtain data on demersal
f inf ish
Obtain data on demersal
f inf ish
Water column
characterization
cruise**
Water column
cnaracterization
cruise**
Determination of
immediate effect of
HCl-HF waste disposal
on seawater
Study of demersal
finfish catches by
by species and station
Determine distribution
and abundance of
benthic invertebrates
Water column
cnaracterization
cruise**
Collected salinity,
temperature, dissolved
oxygen and colitorm
data
Citation
Starr et al.,
197ob
Kolitz et al. ,
I97ba
hazelwortn
ana Darnell,
1970
Azaravitz ,
et al. , I97of
U.S. Dept.
Commerce, 19/5
Hazelworth and
Darnell, 19/u
Starr et al. ,
19/oa
International
Hydronic Corp.
Nov 1974
Azardvitz
et al, I970e
Pearce et al. ,
197ba
Hazeiworth
et ai., iy/5b
EPA, 1974a
li-4
-------
TABLE B-l. (continued)
Date
Mar-May
1974
May 1974
Apr-Jun
1974
Apr-May
1974
Apr-May
1974
Mar 1974
Feb 1975
Mar-May
1974
Jan-Aug
1974
Jan-Feb
1974
Oct-Nov
1974
Sept-Nov
1973
Aug-Nov
1973
Aug 1973
Sponsor/
Investigator
NOAA*/AOML
NOAA*/NMFS
NOAA*/AOML
NOAA/NMFS
NOAA*/NMFS
NOAA*/NMFS
NOAA*/AOML
NOAA*/MSRC
NOAA/NMFS
NOAA*/NMFS
NOAA/MESA
NOAA*/AOML
NOAA*/NMFS
Purpose
Water column
characterization
cruise** with recovery
of bottom pressure
gauges
Fish egg mutagenesis
Water column
characterization
cruise*"
Obtain aata on demersal
f infish
Study of demersal
finfish catches by
species and station
Determine baseline
seabed oxygen
consumpt ion
Water column
characterization
cruise** with deployment
of bottom pressure gauges
To provide aata on sea
surface movements
Collected phytoplankton ,
benthos, heavy metals,
salinity and temperature
data
Study of demersal
finfish catches by
species and station
A study of suspended
particulate matter
Water column
characterization
cruise**
Determine abundance and
distribution of benthic
invertebrates
Citation
Charnell
et al. , 1976
Longwell, 1976
Hazelworth
et al. , 1975a
U.S. Dept. of
Commerce, 1974b
Azardvit z
et al., 1976d
Thomas et ai . ,
1976
Charnell
et al. , 1976
Haruy et al . ,
1976
U. S .Department
of Commerce,
1974a
Azardvit z
et al. , 1976c
Drake ,
1974
Hazelworth ,
1974
Pearce et al . ,
1976b
B-5
-------
TABLE B-l. (continued)
Date
Sponsor/
Investigator
Purpose
Citation
June 1973
i-iay 1973
-June
Oct-Dec
1972
Nov 24,
19/2
Sept
19/1
June 25-29,
1970
Oct 9,
1959
July 2b,
19b7
Summer
1961
Sept Ib-l9,
July 24-
Sept 9,
1956
Oct 195b
NOAA*/NMFS
NOAA*/NMFS
NOAA*/NMFS
Allied
Chemical
New York
Ocean Sci.
Lab.
NL Inaustries/WHOI
NL Industries
NL Industries
NL Industries
WHO I
NL Industries
NL Industries/WHOI
Determine abundance and
distribution of benthic
invertebrates
Study ot uemersal
fintish catches by
species and station
Study of demersal
fintish catches by
species and station
Studies on acid-
fluoride wastes
Determine baseline data
for physical, chemical
and biological
characteristics ol the
New York bight
Detect relationships
between the chemical
and biological
parameters of the area.
benthic study of the
Acid Dump Ground
benthic study ot the
Acid Dump Ground
Determine the fishery
conditions of the area
Evaluate the effects of
acid waste on sport
fisheries
Study the acid grounds
in relation to
certain lisheries of the
area
benthic photo-survey
of the acid waste site
Pearce et al.,
Azardvitz
et al.,
197bb
Azardvitz
et al., 1 y 7 b a
wes tman,
1972
tiYOSL, 1973
Vaccaro,
et al., 1972
Westman,
I9o9
Westman,
1957
Westman,
et al. ,
19bl
Ketchum
et al. ,
Westman ,
I95b
Owen,
1957
b-o
-------
TABLE B-l. (continued)
MULTIPLE-YEAR PROJECTS
Date
Sponsor/
Investigator
Purpose
Citation
June 1974-
June 1975
Aug 197J-
Sept 1974
Aug I9bd-
uec 1971
1965 - 1974
July 19t>4
May 1977
Feb 194c5-
Jan 195U
195U
195U
NOAA/NMFS
NOAA /SHL
NOAA*/NMFS
USAGE/ SHL
USPHS/NETSU
NRG + USFw'S/'.viiOI
+ i-l IT
NL Inaustries/wHOl
USD1
Determine distrioution
ana densities of fisn
Five cruises to aeter-
mine distribution of
benthic invertebrates
Determine distribution
ana abundance of oenttnc
invertebrates
Gollect data to
determine the erlects
of ocean aisposal on
the environment
Historical data on
bivafve molluscs
Gollect coiiform counts
to determine safe shell-
fish fishing grounds
Assess the hyarograpinc
processes of the area
Study the dispersion
rates of barge dis-
charges
Observe effects of
acid-iron waste on
populations
toilk et al.,
19/7
Pearce, et.
al., 1977
Pearce, et al.,
1^7t)c StiL,
iy72; vol. I
SUL, 1972
Kopes and
Merrill, 19/o
Verber, unpub,
Ketcnum,
et ai. ,
Ketchum
6 Fo rd ,
Arnold and
Royce,
Sources:
* Cosponsored with the Marine EcoSystems Analysis Progran (MESA;
** Data collected consisted of salinity, temperature, dissolved oxygen,
nutrients, meteorology, and density.
B-7
-------
TABLE B-l. (continued)
AOML = Atlantic Oceanographic and Meteorological Laboratories
EPA = Environmental Protection Agency
MSRC = Marine Science Research Center
NETSU = Nortn East Technical Support Unit, FDA
NMFS = National Marine Fisheries Service
NOAA = National Oceanic and Atmospheric Administration
MC = National Research Council
SHL = Sandy Hook Laboratory
USACE = U.S. Army Corps of Engineers
USPHS = U.S. Public Health Service
USFWS = U.S. Fish ana Wildlife Service
WHOI = Woods Hole Oceanographic Institution
Project. NOAA's goals were to develop a clearer understanding of the nature
of tne forces driving tnis complex marine ecosystem, and to assess man's
impacts in the area. EPA has concentrated on specific effects of ocean
disposal.
METEOROLOGY
Appendix A summarizes the meteorological conditions in the tiignt.
Conditions at the site itself are, of course, the same as those prevailing in
the Bight. Meteorological conditions in the Bight are not sufficient (.eituer
by themselves or in combination witn other factors.) to preclude or restrict
use of the site for a significant lengtn of time.
PHYSICAL OCEANOGRAPHY
WATER MASSES
water mass characteristics at the Acid Site and in tne bight are generally
the same, except that the site is probably not often influenced by the low
salinity outflow from the Hudson estuary. This water is usually restricted to
tne area west of the Hudson Canyon. Refer to Appendix A for a discussion ot
water mass characteristics in the Bignt.
B-d
-------
CURRENT REGIMES
Hardy et al. (1976) conducted a seabed drifter study to determine the
bottom current patterns in the New York Bight. Sixty nine drifters were
released at the Acid Site and sixteen (23/») were eventually recovered. Eleven
drifters landed on Long Island, five landed in New Jersey; no drifters were
recovered at sea or from within the New York Harbor. It was concluded that
the Hudson Canyon appears to form a boundary of divergence wnere the bottom
drift east of the Canyon (where the Acid Site is located) is northwest to
northeast towards Long Island. The fact that only 23/« of the drifters
released at the site were recovered suggests tnat many of the remainder may
have been trapped in the Hudson Canyon. The canyon is a "trap" for wastes
released at the Dredged Material and Sewage Sludge Sites. Most of the denser
waste components disposed at the Acid Site probably end up in the canyon as
well.
GEOLOGICAL OCEANOGRAPHY
Several reports have examined the sediments of tne New York Bight e.g.,
Stubbiefieid et al. , 1977, Freeland and Merrill, I97t>. In addition, six
reports, Pearce et al. (1977;, Vaccaro et al. U972), All et al. (1973), Owen
(1957)-. and EG&G U978a, I97db), discuss sediments within the Acid Site
boundaries.
The bottom sediments are medium to tine sand, with patches of siity-iine
sand intruding from the northeast (Stubbiefieid et al., 1977). Mean grain
size is 2.dO +J.32 mm for 14 samples taken at two of the MESA sample stations
within the site (.Pearce et al., 1977). Divers have reported tne bottom as
fine sand and silt, overlaid by a flocculent Drown particulate material which
collected in the troughs of ripple marks (Vaccaro et ai., 1972). Owen U957)
reported that the bottom sediments were meaium-grained sand, with greenish-
gray sand predominating. A dark or greenish ooze (.not characterized) was
reported at three sample stations.
EG&G (197da) reported that the surficial sediments varied from gray, to
dark gray, to brown, to dark brown in color. Texture was fine-grained sand,
B-9
-------
round to well-rounded grains, mainly quartz, with a dark mineral assemblage
(glauconite or quartz sand) of } to lU/=. in one case, the sediment was
overlaid by a "soupy" black layer. EG&G U^/ob) reported the bottom surface
sediments as varying in color from brown, to Drown with some biaCK. Texture
was very fine-grained quartz sand, well-sorted and rounded, with some silt
present. Tne presence of a "pasty, tar-like" material is reported in one
sample. None of the investigators analyzed the characteristics of tnese
"oozes," "soups," or "tar-like" material, but speculated tnat tnese materials
may have been sewage sludge, or the slops discnarged from ship's bilges or
fuel tanks.
SEDIMENT TRACE METAL CONTENTS
It has not been consistently demonstrated tnat the sediments within tne
confines of the Aciu Site nave significantly nigner levels of urace metals
than do sediments in surrounding "control" areas. All et al. (.L^]}),
separated the sediments in the liight into four "clusters", on the oasis ol
tneir trace metal content and location. Tne one Acid Site sample tell into
their cluster facies IV, a group containing only a tew, widely separated
samples, and which tne authors were unable to characterize adequately. Iney
suggested that cluster facies IV corresponded to some relict sedimentary
feature of the area. Aside Irom relatively nigh silver (.L7 mg/ i) and lead
(22U mg/1) values, cluster tacies IV was not comparable to their cluster
facies I, which corresponded to sediments sampled at the Sewage Sluage ana
Dredged Material Sites.
Vaccaro et al. (1^72) reported higher concentrations of iron, zinc, cobalt,
copper, lead, chromium, nickel, and cadmium in sediment samples taken from the
Acid Site as compared with a control site. However, tnere is some doubt as to
wiiether these results (.which represent a single suupling time; reflect
statistically significant uifierences between Acid Site and control site
sediments. Samples from the Hudson Canyon contained substantially greater
quantities of these metals than did the samples from either the Acid Waste or
control sites. Vaccaro and nis coworkers U^72) concluded that "...the
implication is that most of tne neavy metal contamination of the New York
Bignt, otner than the iron, is derived from sources otner than the acid-iron
dump."
li-10
-------
fiG&G (I973a) found that zinc, titanium, ana copper concentrations in
sediments from the site were significantly higher than the concentrations at
one reference (control) station. However, copper concentrations from the Acia
Site (2 ppm) and control site (.1 ppm) sediments were more than one order of
magnitude less than those found in otner sediment samples from the iMew York
Bight (bd ppm, range: 21 to o20 ppm tor samples taken between 19oc> and 19/2;
NMFS, 1972), and from other nearshore sites (4o ppm; Chester, I9t>5), Two
sediment samples from the Aciu Site contained titanium; one had a concen-
tration of titanium significantly higher than tnat of tne reference sample,
and one had approximately tne same concentration as the reference sample.
Titanium concentrations in all samples ranged from 71 to 210 ppm. Wiae
variations in zinc concentrations occurred between control site and Acid Site
sediments. In some instances, zinc concentrations at the Acid Site were
significantly higher than those in the reference sediments; at other times,
the reverse proved true. However, all zinc concentrations Grange: 17.i> to
105 ppm), were less than the mean reported for other samples from the New £ork
liight (142 ppm, range: 3 to 900 ppm for samples taken between 19bo ana 1972;
NMFS, 1972).
The fact that significant accumulations of metals have riot been documented
is not surprising. As shown in Appendices C ana D, the relative contribution
of metal contaminants released at the Acid Site is extremely low wnen compared
with the total input to the Apex. Iron and titanium are significant inputs at
the Acid Site, but both of these metals are nontoxic. One toxic metal,
vanadium, is present in high concentrations in the waste. However, within
minutes of discharge into seawater, the vanaaium complexes with otner material
(e.g., other ions, suspended particulates, organic ligands) ana becomes
biologically unavailable. Tne conclusion of Vaccaro"s group (1972) is still
valid: "...there is no clear indication that enhancea disposal activity nas
caused a significant build-up of iron witnin tne sediments immediately below
the acid grounds... Thus, the distribution of iron on the seabottom still
appears to be regulated by natural phenomena."
B-ll
-------
TRANSPORT
Sediment transport away from the immediate area ot the Acid Site can be
derived from bottom topography, current patterns in ttie Bight, and the
distribution of ferric hydroxide particles, whicn are excellent tracers ot
suspended solids originating in the Acid Site. Net transport of coarse
sediment away from the Acid Site is dominated by the "sink" provided oy tne
proximity of tne Hudson Submarine Canyon. Movement towards the Canyon is
accelerated by storm flow transport, wnich is the most important force in
coarse sediment movements. Fine sediments, such as ferric hydroxide
particles, may move nortn towards shore, under intluence ot the surface gyre
(MESA,
Tne Hudson Canyon is the sediment trap for coarse and fine sediments Iran
the Acid Site. The Hudson Canyon also serves as a sink for suspended solids,
sediments originating in other disposal sites, and from the Hudson River
outflow. It is impossible to determine the relative contribution that each of
these sites makes to the total contaminant load reacning tne Canyon.
CHEMICAL CHARACTERISTICS
WATER QUALITY
iG (iy78a) found no significant differences in water column ph values
between tne Acid Site and control samples taken to the northeast, irrespective
ot uepth. In all cases, bottom waters were more acid (p'ti 7.70 to /.do,) than
were surface waters (.pri 8.18 to 8.26). This is normal and is caused by the
oxidation of organic matter. Variations of mean pH values with aepth during
the summer are partially due to density stratification and the presence of a
strong thermocline. Dissolved oxygen levels did not vary significantly
between the Acid Site and control site.
We s ten an Uy58) described the water color in the Acid Site area as green and
somewhat turbid, in contrast with the blue and clear appearance of adjacent
waters. Towards the center of the site, the water color was Drown to brownisti
green. Water discoloration, a characteristic of the site, is the basis for
-------
locating water transport stations during recent monitoring cruises. Tne green
discoloration is caused by the reaction of the ferrous suitate in ML
Industries waste reacting with seawater. As the ferrous iron is oxidized to
ferric hydroxide (.rust), the color changes to a brown to reaaisn prown
(Red field ana Wai ford,
IRON
Ferric hydroxide (.rust) particles, introduced at the Acid bite tnrough
regular disposal activities, provide excellent tracers for the movement ol
suspended waste material away from the site, and indicators of tne degree of
incorporation of waste components in the seuiment or biota (.pelagic and
benthic; biscaye and Olsen, l97t>;. The particles range in size from colloidal
to sand sizes (>62 y) as orange and red aggregates having the appearance of
floccules (.MESA, 1975). Particle distribution varies with deptn in the water
column. Those at the surface are carried by the clockwise surface gyre.
Those near the bottom are under the influence ot the Shelf valley and the
saline bottom water flow towards shore (MESA, 1975;. EG&G U97da) reported no
significant differences in dissolved iron concentrations between the Acid bite
and the control sites.
Iron in Sediments
Table B-2 summarizes data on iron content (ppm> of the Acid Site and
control site sediments. The iron concentrations in sediment are highly
variable, and no clear distinction can be made between the Acid Site and
control site parameters. Acitl Site sediments do not always contain more iron
than do control site sediments; on occasion they contain less. Tne conclusion
from tnese data is that acid waste disposal cannot be consistently related to
the concentration of iron in sediments since other sources are equally
important. Vaccaro et al. (1972) concluded that tnere was no indication of an
increase of iron in the sediments of the Acid Site over a 24-year period
(1946-1972).
B-1J
-------
TABLE B-2. IRON CONCENTRATION IN SEDIMENTS
Sed itnent
Acid Site
Control Areas
Hudson Canyon
Range ot Values ppm
2,200 - 2,500
2,100 - 2,500
y.OOO - 10,000
j,100 - J.200
3,000 - 12,300
0.16/o ash
0.38/o ash
3,100
. 8,300 - o,800
37.000 - 58,000
8,400 - 15,000
2,200 - 3,300
0.15/i ash
Jl ,300
Reference
ERGO, iy78c
EG-icG, 1978c
EGiG, iy?7b
EG&G, ly77c
Vaccaro et al., iy~/2
Vaccaro et al. , iy72
Corwin and Ketchum iy5b
ERCO, ly/oc
EGi.0, iy78c
EG6G, iy78D
EGo.G, ly?7c
Vaccaro et al., Iy72
Vaccaro et al., iy72
Vaccaro et al. , ly/2
Vaccaro et al. (15*72,1, Redfiela and Waltord U^ol), ana Corwin ana Ketcnum
Uy5o> found that the highest concentration of iron occurs in the soft
sediments ot the Huason Canyon. Vaccaro et al. (ly72) suggested that tne
distribution ot iron in sediments was regulated by natural phenomena favoring
an accumulation of fine sediments in the Canyon.
Iron in Biota
Zooplankton - Vaccaro et ai. Uy72,> reported iron concentrations of 120 to
867 ppm in dried samples of zooplankton taken from the Acid Site and
concentrations of 130 to 380 ppm iron in similar samples taken at a control
site. Zooplankton from an oceanic site 120 km south of tne Acid Site
contained 730 ppm iron. It was concluded that the iron precipitated in the
discharge area does not appreciably affect the zooplankton. Ketchum et al.
(ly58) found that the intestines of zooplankton collected in the discolored
water of the Acid Site were packed with precipitated ferric hydroxide
particles. Following a series ot feeding experiments, it was further
concluded that the particles were passed through the intestinal tracts of the
animals with little or no change, and apparently without, harmful effects.
B-14
-------
Vaccaro et al. (1^72) reported iron concentrations ot 6,dUO and 22,000 ppm
in two ashed samples of benthos from the Acid bite, and 2, yOU ppm in a sample
from a control site. A sample from the Hudson Canyon contained 5,60U ppm
iron. Tnese data suggest that iron may be accumulated by the benthic biota ot
tne Acid Site. However, it is not possible to test this conclusion
statistically, since replicate samples were not taken at the control site.
Nekton - Westman (1956) analyzed the stomacn contents ot ten cnub mackerel
(Pneumataphorus colias) , five taken in the water of the Acid Site, and five
taken near the waters of the Dredged Material Site. He reported tne following
values:
Stomach Contents
iron content (mg)/ stomacn
Percent iron in total stomach contents
Percent asn
Total contents (mg) /stomacn
Dreager: Material Site
u.J7
u.6t>
4.ua
J/.l
Acid Site
J.i
U.4/
5.UJ
744
These data do not clearly indicate that iron was assimilated by the lish,
since differences in stomach iron content could be due entirely to tne great
variations in total stomacn contents.
BIOLOGICAL CHARACTERISTICS
WATER COLUMN BIOTA
Vaccaro et al. (1972) found zoopiankton biomass (.both in terms of dry
weight and displacement volumes) to be approximately 307, higher in the control
area than in the area of the Acid Site. Tnis difference could be due entirely
to the patchy distribution of zoopiankton in the Bight.
Wiebe et ai. (197J) were unable to observe a trend in the spatial distri-
bution ot zoopiankton which would suggest that acid wastes were an important
factor in forming such distributions. Gibson 11973) concluded that "...under
present conditions the disposal of acid waste ... in the New York Bight is
having no discernible effect on the local zoopiankton population."
B-ii
-------
Longwell (1976) found that developing mackerel eggs, collected from the
waters near the Acid Site, snowed an appreciably Higher incidence of
chromosome abnormalities (.60.6%, compared to a control site value of 12.7/0,).
A sample taken southwest of the Acid Site showea Jd.o/i abnormalities while a
sample taken to the south showed 52.1/o abnormalities. Longwell implied that
these abnormalities were clue to the mutagenic properties of heavy metals.
Chemical mutagenesis of fish egg chromosomes was tirst suggested by Kinne anu
Kosentnal (1%7) in their studies of sulfuric water pollutants anu larvae of
the Atlantic herring, Clupea harengus . However, danger to fish eggs was noteu
only up to a dilution of waste by ocean water of 1:32,000 UNOAA, 1972).
Minimal dilution of acid waste after initial mixing is l:o7,UOO (ERGO, ly?da).
Westman (1953, 1%7, and 19o9) reported that acid waste disposal actually
enhances fishing in the Acid Site area. The "acid grounds" did not exist as a
recognized fishing area until acid waste disposal started. It was concluded
that darkening of the water (increased turbidity) due to the presence of
suspended iron particles provided a sheltering environment attractive to
fishes, particularly bluefish.
Trawl data (Table B-J ) obtained by Wilk et ai. (19/7) do not clearly
substantiate Westman1 s belief tnat there is improved fishing at the "acid
grounds." These data are highly variable and do not indicate whether there is
an impoverishment or enrichment of fish populations at the Acia bite.
Swanson (1977) concluded that although "... observational evidence of the
impact of dumping on tne biota at the (site,) is limited.... past studies
indicate no reduction of primary productivity or phytoplankton mortality....
surveys of benthic populations in the immediate vicinity of the Apex Acici
Waste Uumpsite have not demonstrated an observable impact of waste acid....
existing scientific evidence indicates so tar that ocean dumping i,of waste at
the acid-waste disposal site) has had minor adverse impacts on the ecology."
BENTHIC BIOTA
Much quantitative data on benthic biota of the Acid Site is summarized in
Table B-4. Tnere is no consistent trend in species diversity values (A'), ana
-------
TABLE B-3. FISH IN THE VICINITY OF THE ACID WASTE SITE
(mean + std. dev.)
Area
Acid Site
Near Acid Site
Control site
Number
of samples*
3
6
5
Number
of individuals*
201 +_ 172
114 + 69
511 + 255
Weignt
of catch (kg)*
26.6 + 32. J
47.0 +. 52.8
101.2 +_ 47.6
Number
of species*
11+4
11 +_ 3
13 _+ 4
* +_ One standard deviation
no clear indication that the benthic fauna of tne Acid Site are particularly
enriched or reduced, with respect to surrounding control areas. however,
Vaccaro et al. (1972) did find significant differences between mean densities
of benthic animals at tne Acid Site and control site. Kowe U971) noted that
there was a decrease in the species diversity values from deep water towards
the Acid Site, and that values for the Acid Site were lower than those in the
control area. Evaluating tne data from Pearce et al. (.1977.), showed that
differences in mean diversity values from the Acid waste Site and control site
were not statistically significant. These data did not demonstrate any
significant geograpnic trends wnich would support the findings of Rowe (1971).
Pearce et al. (1976d) noted that tnere is a close correlation between the
distribution of benthic organisms and sediment type, yet no correlation was
found between the diversity value and either mean grain-size or percentage of
organic material in 61 samples taken at MESA sampling sites in the bight.
However, two low-value samples from within the Acid Site were associated witn
high values for percentage of organic material. These findings and otners in
Table b-4 support the general conclusion that tnere is a high degree of
spatial and temporal variability in the benthic fauna of the New York bight
(Pearce et al., 1976d) .
b-17
-------
TABLE B-4. COMPARISON OF SPECIES DIVERSITY AND
ABUNDANCE VALUES FOR ACID WASTE AND
CONTROL SITES IN THE NEW YORK BIGHT
Site
Control
Acid bite
Acid Site
Acid Site
Acid (pre-dump)
Control (pre-dump)
Acid (post-dump)
Control (post-dump)
Control (35 samples)
Acid (14 samples)
Coastal (10 samples)
S
-
6
7
7 .
7
b
b
7
5
y
2
4
4
-
N
2y64/m2
1694 An2
73 +
120 +
72
21
24
J7 +
60 +
104 +
512
Jd
546
17»
-
ri '
2.13
2.06
0.67
0.56
1.15
1.20
i.jy
0.60
l.oa
0.24
i.jy
O.b3
o.y4
0.76
2.06 + O.yi
1.55 +_ U.87
1.65 +_ U.52
Source
Vaccaro et al., ly72
westman, ly6/
Westman, 1 yoy
Arnold and Uoyce, ly5U
Fearce et al. , iy77
H1 = Shannon-Wiener species oiversity index
N = Total number ot individuals
S = Total number of species
-------
Appendix C
CONTAMINANT INPUTS
TO THE NEW YORK BIGHT
-------
CONTENTS
Page
SOURCES
-------
Appendix C
CONTAMINANT INPUTS TO THE NEW YORK BIGHT
Large volumes of waste discharge enLer the bight Apex by direct disposal
operations, e.g., barge disposal, coastal discnarge, rivers, or outtail
effluents. Indirect waste inputs, e.g., atmospheric fallout, add to the total
(Figure C-U . The largest single source of discharge (by volume; into tne
Apex region derives from the New Yonc Harbor across the Sandy Hook-Rockaway
Point Transect (Mueller et al . , 1^76).
Acid waste introduces a limited variety of contaminants to tne New York
bight — several trace metals found in inorganic acids and compounds, suspended
solids, and oil and grease (Figure CJ-1 ) . Consequently, the discussion of
contaminant inputs to the bignt is restricted to these same contaminants and
an analysis of the relative contribution of sources other than tne Acid Site.
In this Appendix, the relative contribution of sources of contaminants will
be examined and, based on the available data, the mass Loading (. amount,) ot
these contaninants will be estimated for the bight Apex. Trace metals are
important contaminants. Some trace metals (e.g., lead and mercury), are
extremely toxic to living organisms. Others, namely chromium, copper, and
zinc are essential to Life processes of living organisms, but may be toxic in
nigh concentrations or in certain chemical forms (Segar and Cantillo, 1975J.
Cadmium, chromium, and mercury are discussed because ot their significance as
toxic contaminants. Iron, the principal metal contaminant introduced with
acid wastes, is a fairly nontoxic metal, but its release in large quantities
may influence activities of other more toxic metals. Suspended solids are
discussed because of their importance in trace metal transport to, and removal
from, waters of the Apex. Oil and grease, which cause chronic effects on
organisms, are present in the waste.
In iy?b, a panel of marine experts identified contaminants that are, or are
likely to be, the most serious problems in the Bight (MESA, 1976) . In
comparing contaminants present in acid waste with those identified by the
C-l
-------
o
I
ho
PARAMETER
FLOW, MOD
SUSPENDED SOLIDS
OIL & GREASE
CADMIUM
CHROMIUM
COPPER
LEAD
MERCURY
ZINC
LOAD
METRIC TONS/DAYS
19,386
23,580
783
2.43
5.26
13.20
12.40
0.52
32.10
PERCENTAGE CONTRIBUTION
40 60
80
100
TRANSECT ZONE LONG ISLAND (2) ATMOSPHERE (3) DREDGE MATERIAL SEWAGE SLUDGE
CELLAR DIRT
]. FOLLOWING THE TRANSECT ZONE, ALL REMAINING CONTAMINANT SOURCES
CONTRIBUTE ONLY ABOUT 0,5Z OF THE TOTAL DAILY VOLUME.
2. LONG ISLAND CONTRIBUTES ONLY CHROMIUM ABOVE THE 0.5* LEVEL.
3, ATMOSPHERIC INPUT HAS EEEII ESTITATED BY DUCE ET AL.J ]S76, FOR
SUSPENDED SOLIDS., CADMIUM., LEAD AND ZINC OVER AN AREA
-------
experts, only mercury and cadmium are considered to be "major perceived
threats." Arsenic, chromium, and lead are considered to be "substances not
requiring priority attention", thus most of the contaminants discussed in this
Appendix are not even considered to be potential problems and, as documented
in Appendix D, acid wastes are insignificant sources of the five trace metals
mentioned.
This Appendix is divided into three sections. The first section briefly
describes the sources of contaminant inputs to the bight, and the second and
third sections present the same data, from different viewpoints. Tne second
section discusses each source and the contaminants it provides, while the
third discusses the contaminants in terms of the major sources.
SOURCES
Five sources of contaminants are considered in tnis section - tne Transect
Zone (representing outflow from New York Harbor,) , barged ocean waste disposal,
atmospheric fallout, surface and effluent discharges from New Jersey and Long
Island coastlines (Figure C-2) . The Transect Zone contributes over 9yx» of the
total volume while barged wastes and for some metals, atmospheric fallout are
important sources of contaminants.
Tne information presented in this section is based largely on data
presented in Mueller et al. U97t>); nowever, reliability of these data has
been questioned by Lee and Jones (1977). According to Lee and Jones, the
estimated quantities of dredged material contaminants reported by Mueller et
al. (1976) are of questionable accuracy. The information presented by Mueller
et al. (1976) represents the best data presently available tor total Apex
contaminant input estimates, although contaminant input estimates for dredged
material may be inaccurate. Lee and Jones (1977) cannot state if tnese
estimates are high or low for each contaminant. Furthermore, Lee and Jones
(1977) point out that contaninants are not entirely released into receiving
water when dredged materials are disposed, hence Mueller's estimates represent
the worst-case condition. C\
(J-J
-------
A DREDGE MATERIAL
O MUNICIPAL SLUDGE
D ACID WASTE
• RUBBLE
NAUTICAL MILES
Figure C-2. Geographical Zones in the New York Bight
(from Mueller et al., 1976)
TRANSECT ZONE
The Transect Zone of the lower New York Harbor is delineated across the
channel entrance, from the tip of Sandy Hook peninsula to Rockaway Point. New
York Harbor is fed by numerous rivers of New York and New Jersey. The Hudson
River and its drainage basin is the largest source of water to the lower bay,
2
and it drains approximately 34,630 km . The Hackensack, Passaic, and Raritan
2
Rivers in New Jersey drain approximately 6,790 km .
These rivers and their tributaries provide most of the municipal and
industrial water requirements of approximately 15 million people (Mueller et
al., 1976). Most contaminants in these waters ultimately reach New York
Harbor and enter the New York Bight Apex either by the surface outfljofc across
the Transect or by dredging operations which release materials at the Dredged
Material Site.
G-4
-------
OCEAN DISPOSAL SITES
Ocean disposal of waste materials within the flew York. Bight started before
1900. The Acid Waste Disposal Site was designated for use in I94d. Other
sources of great volumes of waste materials are the Dredged Material Disposal
Sites; the first DMDS was designated in 1883. The Dredged Material Disposal
Site considered here has been in use since 194u (.Gross, 1976J. The Sewage
Sludge Disposal Site was first used in 1924 and the Cellar Dirt Disposal Site
was established in 1940. Large volumes of trace metals, suspended solids,
organic wastes, and nutrients are introduced into the marine environment at
tnese sites.
A fifth site, located over the Hudson Canyon at the edge of tne Apex, is
used for disposal of wrecks. Only eight ships have been reported sunk at this
site, and none since 1973 (EPA, 1978.). Since tne ships are stripped of
potential contaminants prior to disposal, this site does not measurably
contribute to anthropogenic inputs to the Bight.
Two disposal sites are beyond the Apex of the New York Bight. A sixth site
was designated for toxic chemical wastes in 1965. however, tnis site is
106 nmi southeast of Ambrose Light at the edge of the Continental Shelf. The
106-Mile Chemical Uaste Site is, therefore, outside the sphere of influence of
the inshore Apex region. An area south of the Apex (at approximately 4u"N,
73°40'W) has been used for the incineration of driftwood, harbor pilings, and
other wood debris from harbor wharf construction. Possible contaminants from
this source can be neglected since the site is outside the Apex and the
burning does not affect the water column, with the possible exception of
minute amounts of atmospheric loading. The ash and other residue is returned
for land disposal.
ATMOSPHERE
Contaminant inputs from the atmosphere have only recently been evaluated.
Estimates provided by Duce et al. (1976) are basea on samples taken frvear the
New Jersey and Long Island coasts of the Bight (Table C~l)- Their estimates
C-5
-------
are calculated on the assumption that no atmospheric contaminant gradient
occurs from nearshore to the outer Bight, i.e., atmospneric concentrations of
contaminants are equally dense at 100 km offshore and at 1 kin offshore.
Settling velocity estimates ol atmospheric particles do not conform to tnis
assumption. Duce et al. Uy7t>) concluded that their calculations prooably
overestimate metal inputs from atmospneric fallout. Direct measurements of
trace metal inputs throughout the New York bignt are required for reasonably
accurate estimates of atmospheric source loading by precipitation and dry
fallout. These measurements snould include at least one seasonal cycle.
Uuce anu Hoffman (.1^76.) concluded that as much as I0/o of the total antnro-
pogenic vanadium injected into the atmosphere in i'Jorth America may be
deposited in the central Nortu Atlantic by northern hemisphere westerlies.
Three models, which may be accurate only to within one oraer of magnitude,
were compared in deriving this estimate.
TABLE C-l. TOTAL MASS LOADING - NEW YORK BIGHT APEX
(Tonnes/Day)
Input
Tranaect
Zone
Ocean ^
Diapoaal
Atnoapheret
Long !• land
Coaatline
Total
Cadmium
0.36
2.04
0.03
<0.01
2.43
1
Contrib.
14.8
83.9
1.2
<0.5
Chroniun
2.2
3.03
ft
0.03
5.26
I
Contrib.
41.8
57.6
—
0.5
Copper
6.2
7.0
tt
0.01
13.2
I
Contrib.
47.0
53.0
—
<0.5
Iron
35.0
180.0
6.1
0.6
221.7
I
Contrib.
16.0
81.0
3.0
<0.5
Mercury
0.26
0.26
tt
<0.01
0.52
%
Contrib.
49.9
49.9
—
^0.05
Lead
5.8
5.4
1.2
cO. 01
i
h
Z
Contrib.
46.8
43.5
9.7
<0.05
. Zinc
17.0
9.1
5.9
0.1
32.1
I
Contrib.
52.9
28.3
18.4
<0.5
Sourcea:
* All eatinatea, except atnoapheric, from Mueller et al., 1976.
t Duce et al., 1976.
** Include! all ocean duping activitiea.
tt Not meaaured.
C-6
-------
Atmospheric input of most metals is an insignificant contribution in
comparison to the Transect Zone and ocean dumping (Table C-l). Tnis source or
input can be neglected when evaluating the effects of contaminants in the
Bight because of tne diffused input from this mode of contaminant entry.
NEW JERSEY
Contaminant inputs along the coast of New Jersey were examined by Mueller
et al. (1976.). They listed 5 industrial wastewater sources, 50 municipal
wastewater sources, ana surface runoff water contaminants. Contaminants in
groundwater are included in t"he surface runoff.
Tne Mew Jersey coastline is an unimportant source ot contaminants (Table
C-2). Mueller et al. (ly76) reported values only from the coast soutn ot tne
Shark River (at the edge of the Apex). Contaminants north of the Snark River
are included in the Transect Zone figures. Surface currents usually move
south along the New Jersey shoreline (see Appendix A), thus contaminants are
transported out of tne Apex and do not add to its contaminant load.
Therefore, New Jersey coastline contaminants are not included in total mass
loading figures in Tables C~l and C-4.
LONG ISLAND
Contaminant sources along the Long Island coastline were examined by
Mueller et al. (1976), including sources between Pines brook in western Nassau
County and Montauk Point. Six municipal and 20 industrial (duck farm) waste
sources were considered in waste loading estimates. Groundwater produced a
significant flow, but contained insignificant waste loads.
Approximately d5/» of the Long Island coastline is beyond the borders of the
Apex. Therefore, in evaluating Long Island's importance as a contaminant
source, a linear relationship between the total contaminant loading from Long
Island coastline and tnat portion of tae coastline inside the Apex region was
included. Table C-j represents the estimated total average uaily input
C-7
-------
TABLE C-2. CONTAMINANT INPUTS FROM THE NEW JERSEY COASTLINE
(Tonnes/Day^
Input
Volume (MGO)
Suspended Solids
Oil and Grease
Metals
Uadin iurn
Chrocuiuni
Copper
Iron
Mercury
Lead
Zinc
Municipal i*
Industrial
Wastewater
105
55
6.6
0.0036
0.026
0.057
0.22
0.017
0.055
0.067
Surface
Runoff
3,300
79
69.0
0.0034
0.0064
0.0b5
5.2
Nil
O.U12
0.2(3
Total
3,400
134
75. b
0.012
O.OJ2
0.12
5.4
O.U17
O.Uo7
0.33
Source: From Mueller et al., 1976
TABLE C-3. CONTAMINANT INPUTS FROM THE LONG ISLAND COASTLINE
(Tonnes/Day)
Input
Volume (MGD;
Suspended Solids
Grease & Oil
Metals
Cadmium
Chromium
Copper
Iron
Mercury
Lead
Zinc
Municipal &
Industrial
Wastewater
d8.0
11. J
4.6
0.00091
0.19
0.024
0.096
0.0017
0.014
0.66
Sur lace
Runoff
225.0
5.4
0.55
0.00066
0.0005
0.0036
0.27
Nil
0.0052
0.022
Groundwater
230.0
0.0
0.0
0.00003
0.0
0.0009
0.023
Nil
0.0003
0.0024
Total
59J.O
lo.7
5.4
0.0016
0.19
0.029
0.39
0.0017
0.02
O.bci
Source: Mueller et al., 1976.
C-8
-------
TABLE C-4. TOTAL MASS LOADING - NEW YORK BIGHT APEX
(Tonnes/Day)
Input
Transect Zone
Ocean Disposal
Atmosphere
Long Island Coastline
Total
Volume
CMGD;
19,291
10
NA
35
19,3S6
Percent
Contrib.
99.5
0.5
—
0.5
Suspended
Solids
7,300
15,11)8
1,170
2.4
23,530
Xo
Contrib.
31. 0
64.0
J.U
0.3
Oil t*
Grease
460.0
322.0
0.0
0.7
732.7
/«
Contrib.
59.0
41.0
O.U
0.5
Source: From Mueller et al., 1976.
contributed by the entire Long Island coastline. Tables C~4 and (J-l represent
one-seventh (15/»J of the total contribution, estimated to be entering the Apex
region from the Long Island coastline. Although currents may oring
contaminants from eastern Long Island into the Apex, at other times currents
will flow eastward and remove contaminants from the Apex. In eitner event,
Long Island is an insignificant contaminant source.
MASS LOADS BY SOURCE
TRANSECT ZONE
Mueller et al. (1^76) estimated the average volume of contaminant loaded
water entering the New York Harbor complex from industrial, municipal, urban,
ana surface runoff to be 350 m per second. This volume and the estimated
contaminant mass loads are derived via mean sample values from various records
(government, industrial and academic) tor the period l^bO to iy/4 (.Table C-5).
Surface runoff contributes approximately 46£ of the average daily volume,
industries contribute 14/i of the daily average, and urban discnarge
contributes about 40/£ of the total.
C-9
-------
TABLE C-5. CONTAMINANT INPUTS FROM THE TRANSECT ZONE
(Tonnes/Day)
Input
Volume (MOD)
Suspended Solids
Oil and Grease
Metals
Cadmium
Chromium
Copper
Iron
Mercury
Lead
Zinc
Municipal £»
Industrial
Wastewater
2,700
870
193
0.14
0.92
2.73
12.95
0.2U
2.67
3.23
Surface
Runoff
15,430
3,500
64
0.1U
0.51
1.24
9,10
0.04
0.75
6.46
Urban
Runoff
1,160
2,900
202
0.12
0.77
2.23
12.95
0.02
2.3d
7.31
Total
19,^91
7,300
400
0.36
2.2
6.2
35.0
0.26
5. a
17.0
Source: From Mueller et al., 1976.
Suspended solids constitute the largest amount (by mass) of contaminant
materials. The river-suspended load is the single largest source, approxi-
mately 3,500 tonnes/day (4d/0), and urban runoff contributes 40/i of the total.
Industrial discharge of suspended solias averages only 12/o of the contribution
(approximately 870 tonnes/day). Urban runoff (44/O and municipal/industrial
wastewater (42/O are the main sources of oil and grease.
Tne input of cadmium (.Table C-5) is evenly distributed among the three
effluent categories: municipal and industrial wastewater, surface runoff, and
urban runoff. Inputs of zinc are nearly equal between surface runoff (387.)
and urban runoff (43/»).
Industrial and municipal discharges, combined with urban runoff, contribute
about three quarters of the total input of other metals. The former averages
about 42% of the total input, and urban runoff is about 37/£ of the total.
C-10
-------
An estimated 35 tonnes of iron is discharged into the New York Harbor aaily
(Mueller et al., iy?6; Table C-5). This is the largest amount among all
metals studied. Other metals with high inputs are zinc and, to a lesser
extent, lead and copper.
Sediments of the harbor complex are not considered here because tneir
contaminants are immobilized, and thus do not influence the Apex region.
Harbor sediments are an important contaminant source wnen dreagea and released
at tne Dredged Material Site.
OCEAM DISPOSAL
hueller et al. (1976) examined the volume of material aropped at tne Dredge
Material, Sewage Sludge and Cellar Dirt Sites (Table C-fc>; . The largest volume
of waste material is released at the Dredged Material Site, wnich receives
approximately 24,1UO m /day, or 64.5/» of the daily average of material dumped
at the three sites. The Sewage Sludge Site receives approximately Jl.d/i
2
(Il,rf20 m /day; and the Cellar Dirt Site receives approximately 3.//<, U.354
m3/day).
The greatest volume (d6£) of suspended solids is introduced at the Dredged
Material Site (Table C-t>) . Mueller's group estimated tuat tne Cellar Dirt
Site contributes about 1,300 tonnes/day, or III of tne total suspended solid
load, but the amount is probably only about 3UU tonnes/day, or only 2/, of the
total (Interstate Electronics Corp., 197d). The oil and grease input is
primarily from dredged material disposal, with approximately 300 tonnes/day
entering tne Apex (93/i of the total) .
For the metals, the Cellar Dirt Site is an insignificant source and the
Dredged Material Site contributes from 50/i to 96/i of all metals examined
(Table C-6). Except for mercury, the Dredged Material Site contributes an
average of 86% of the metals, and the Sewage Sludge site the remaining 14£.
Iron, copper, lead, and zinc are significant contaminant inputs from direct
ocean disposal.
C-ll
-------
TABLE C-6. CONTAMINANT INPUTS FROM OCEAN DISPOSAL
(Tonnes/Day)
Waste Type
Dredged Material
*
Sewage Sludge
Cellar Dirt
Total
Volume
(m /day)
24,100
11,820
1,364
37,284
Suspended
Solids
13,000
450
1,650
15,100
Oil and
Grease
300
22
—
322
Cadmium
2.0
0.044
—
2.044
Chromium
2.3
0.73
—
3.03
Copper
6.3
0.70
—
7.0
Mercury
0.013
0.013
—
0.026
Lead
4.7
0.72
—
5.42
Zi nc
7.3
1.8
—
9.1
*1973 Data only
Source: From Mueller et al. (1976)
-------
Approximately 0.026 tonnes/day of mercury is deposited at the Dredged
Material and Sewage Sludge Sites combined (.Half ot the total at each site;.
However, due to the larger average daily volume of dredgea material, these
values suggest that sewage sludge is more nighiy contaminated with mercury.
Mass loading estimates of iron at these sites was not calculated by Mueller
and his co-workers, but an estimate of loading from all dumping activities
(including the Acid Site, which is the most significant source of iron) is
given as IbO tonnes/day. MESA (1975) estimated that the Acid Site ana outflow
from the Transect Zone contained about equal amounts of iron. MiiSA (ly73)
concluded that the three prominent sources of most metals are tne Dreaged
Material Site, the Sewage Sludge Site, and the Transect Zone.
ATMOSPHERE
Tne potential atmospheric transport of trace metals into the water ot tne
New York Bight has only recently been examined. Duce et al. Qy7b) measured
atmospheric metal concentrations from samples taken over a 1U,GUU km area ot
the bight. It was found that atmospheric concentrations were generally lu to
20>i of the mean concentrations observed at several locations in Wew York City
over a 2-year period.
Samples collected by Duce et al. (.1976) indicated that the quantities of
metals entering the Apex from the atmosphere are considerably less than those
from all otner sources (see Table C-l). Lead, for example, is 15/» of tne
total from the previous two sources but cadmium is only 1/i of the total, ury
fallout values are based on sample observations. Wet fallout values
(primarily rain) are based on an estimate ot 67X» removal factor, thus wet
fallout is given as double the dry fallout. Duce and his co-workers
emphasized that these estimates of atmospheric transport may be high, by a
factor of five or more. Long term studies are required to produce reasonably
accurate values. However, since the absolute input is low, these are
sufficient data for this EIS.
C-U
-------
Mueller et al. (.1976) calculated input values for airborne metals using
measured data collected in a one-year study from the Upper Great Lakes (Table
C-7). They considered the entire New York Bight, approximately J9,UOO km ,
for estimation purposes. Thus, their input estimates consider an area four
times the size sampled by Duce et al. (1976). Comparison of Mueller's
estimates to Duce's estimates shows that Mueller's are lower by a factor of
about 9 (Table C-7). This emphasizes the approximate nature of these values.
Estimates reported by Duce et al. (197b; are used in this report since
these data represent direct source measurement from the area of interest. The
primary factor limiting the use of these oata is the tact that they represent
a small sample from a short sampling period and are, at best, rough estimates.
The sources of these metals are both natural and anthropogenic.
Northeasterly and southeasterly winds blowing across the mainland accumulate
large quantities of iron in soil, smoke, and ash. Iron is the most abundant
metal present. Levels of zinc may be the result of a similar accumulation
process.
Atmospheric lead is derived from the combustion of leaded gasoline in
internal combustion engines (Zoller et al., 197J) and would tnerefore be
expected in significant quantities.
TABLE C-7. CONTAMINANT INPUTS FROM ATMOSPHERIC FALLOUT
(Tonnes/Day)
Input
Dry Fallout
Wet Fallout
Total (Duce
et al., 1976)
Total (Mueller
et al., 1976)
Cadmium
U.01
0.02
0.03
0.054
Iron
3.40
6.ao
10.20
6.10
Lead
U.55
1.10
1.65
1.20
Zinc
0.74
1.9d
2.72
5.90
C-14
-------
Atmospheric cadmium (for example, from the wear of automobile tires> is
present in minute quantities. The source of contamination is not apparent, it
may be either natural, anthropogenic, or a result of combined sources.
NEW JERSEY COASTLINE
Contaminant sources from the New Jersey coastline are restricted to two
major categories: municipal ana industrial wastewater, and surface runoff. In
terms of volumes, surface runoff contributes more than 30 times tne average
amount of municipal and industrial wastewater. Bui: municipal and industrial
waters often contain more concentrated amounts of specific contaminants (Table
C-2).
Suspended solids are about equally divided between the two sources.
Municipal and industrial wastewaters contain approximately 41/« of the average
daily total. Surface runoff contains about 79 tonnes/day. or 5^ of the
total. Oil and grease is primarily from the surface runoff (.yl/i of the
total) .
In metals derived from surface runoff the results are: cadmium (70/c of the
total), copper (54/O iron (96 percent), and zinc (79/o); but primarily found in
municipal and industrial wastewater are: chromium (8LU), mercury (lUU/»>. and
lead (72/i).
Iron is found almost exclusively in surface runoff. The amount represents
about 96% of the average daily total. This implies that the sources of iron
are significantly natural, and man's activities contribute iron insignifi-
cantly. Mercury is found exclusively in municipal and industrial wastewater.
This implies that the mercury contamination is entirely from anthropogenic
sources along the New Jersey coastline.
These mass load estimates are provided for comparative purposes only.
because these data from the New Jersey coastal region are outside the Apex
region and the contaminants are transported to, or deposited in, other areas
of the New York Bight.
C-15
-------
LONG ISLAND COASTLINE
Contaminants introduced into the New York Bight from tne Long Island
coastal area are mainly from municipal and industrial wastewater discharge
(Table C-3). Surface runoff and groundwater sources contribute minor amounts
of most contaminants. The total volume of discharge averages approximately
2,24ii m (593 MGD). Of this volume, approximately 15% is of municipal ana
industrial origin. About 38% is surface runoff, and 47% (i,U5p m ) is ground
water.
Sixty-eight percent of suspended solids are from municipal and industrial
wastewater; the remainder is discharged with surface runoff. Groundwater does
not contribute to the suspended solids load. tlighty-nine percent of the oil
and grease is carried by wastewater and the remainder in the surface runoff.
The levels of metal contaminants are low; the majority of the metals are
found in the wastewater discharges. Surface runoff contributes an appreciable
amount of cadmium (4i%) iron (69%) and lead (2b%). Groundwater discharge to
the Bight contains low levels of all metals and it contributes only sligntly
to the iron load (6% of tne total amount). Natural sources of iron are the
most important inputs (75% of the total).
TOTAL MASS LOADING OF THE NEW YORK BIGHT APEX
This section evaluates tne total mass loading of contaminants entering the
Apex of the New York Bight. Virtually all potentially contaminated material
entering the bight passes through the Transect Zone. Ocean disposal
operations are low in volume (less than 0.5% of the total), but contribute a
higher proportionate contaminant volume. Dredged material disposal
contributes most of the suspended solids. The fate of suspended solids in the
Bight is complex and still not well understood. They are important because
trace metals and other contaminants are adsorbed by them; these "secondary"
contaminants may enter the food chain, either directly via filter feeding
shellfish, or indirectly via the plankton.
C-16
-------
Monitoring of trace metal contamination is important because of known toxic
effects on immans and on the normal biota of the area. Ocean disposal of
dredged material and sewage sludge is, in general, tne predominant source of
metals, and the Transect Zone source is almost equal. Since dredged material
is contaminated by tne settling of riverborne particles carried into tne
Harbor, the problem of reducing the oceanic loading cannot be separated from
reducing the river load. The Acid Site contributes minor anounts of all trace
metals except iron (see Appendix D). In the same manner most oil and grease
is released at the Dredged Material Site or is part of the outflow through the
Transect Zone.
VOLUME
The following estimates of tne contaminant volumes entering the liight are
based primarily on reports by Mueller et al. Uy76j and Uuce et a.l. U976,).
Some sources, such as municipal and industrial wastewater, surface runoff, and
ocean dumping are well documented by EPA and Army Corps of Engineers
monitoring programs. The least reliable estimates are atmospheric inputs,
urban runoff, and groundwater discharge, either because of the difficulty in
measurement or simply a lack of sufficient data (.Mueller et al., 197b>).
The Transect Zone contributes almost all the potentially contaminated
water, 99>o (.Table C-4>- However, not all the contaminants which enter the
harbor complex are eventually transported to the Apex region. Some of tuis
material probably settles within the harbor where it remains until disturbed
and resuspended. Greig and McGrath (1977) concluded that three "metal
regimes" existed within Raritan Bay. Western Raritan bay is an area of nigh
metal concentrations. Concentrations diminisn towards the lower New York
Harbor area and reach their lowest values (near background levels; at the
Harbor entrance (tne Transect). However, much of the contamination from the
riudson River is transported to the Dredged Material Site in tne bight when tne
harbor and channels are dredged.
C-17
-------
The Long Island coastline contributes tne second largest volume of
discharge (Table C-4). The data collected by Mueller et al. U*7o) for the
Long Island ana New Jersey coastlines include areas well beyond the Apex
region. Consequently, a1 large portion of the contaminant inputs from tnese
sources enters the Bight Outside the Apex. Data reported by Mueller's group
have been modified in Tables C-l and C~4 based on the assumption tnat tnere is
a linear relationship between the amount of a given contaminant and the length
of tne coastline. Thus1* since approximately one-seventn of Long Island's
coastline lies within the "Apex, tne contaminant input values for Long island
are divided by seven. Thfs -'may result in a somewuac low estimate of tne mass
loading occurring in the Apex from the Long Island coastline. Except for the
Shark River (at the edge.) , the rest of New Jersey's coastline is outside the
Apex. Accordingly, contaminant inputs from New Jersey are not included in
total mass loading estimates of the Apex. Anotiier assumption is tnat water
motion is directed away from tne Apex region along the coastlines. For New
Jersey, this assumption is valid; surface waters tend to move soutn along tne
coast. Long Island coastal waters may move westerly into the Apex. However,
most of the surface runoff and wastewater discharges are into Great Soutn bay
and thus, most contaminants settle to the bottom and are not transported into
the Apex.
Ocean dumping provides the smallest volume of all sources, although it is a
very important contaminant source, particularly for trace metals. Ocean
disposal ranks first or second in percentage contribution for all the
parameters examined.
SUSPENDED SOLIDS
Suspended solids are organic and inorganic particulate matter in water
(EPA, 1976), which may contain both biogenic and non-biogenic debris (biscaye
and Olson, iy?6).
Table C-4 and Figure C-l illustrate the relative contrioution of suspended
solid contaminant sources. Ocean disposal (principally ureciged material and
cellar dirt) is the largest source of suspended solids, approximately two
-------
thirds of the daily average. This estimate is high because the value used oy
Mueller's group in estimating cellar dirt contribution (Table C-4J assumed
that all material released at the Cellar Dirt Site was suspended solid
material. In 1974, approximately half of the cellar dirt was material six
inches or larger; the estimate by Mueller's group is at least 5lU too nigh.
Interstate Electronics Corp. (197tf) estimated that suspended solids amounted
to only about JOG tonnes/uay trom 1973 to ly77 at the Cellar Dirt Site. Even
if Interstate1 s estimate is more accurate, the total daily loading of
suspended solids by ocean disposal will be reduced by less than lu/i. This
correction still leaves ocean disposal as the singU largest contributor of
suspended solids.
The Transect Zone provides the second largest source of suspended solids,
or about a third of the daily average. Atmospheric fallout contributes the
remaining amount; the Long Island coastline contribution is insignificant.
DREDGED MATERIAL AND THE TRANSECT ZONE
Gross (1970, 1976.) examined New York Harbor sediments. Metals and other
contaminants are adsorbed by particles which, as they settle in the harbor
complex, remove these contaminants from the water column (.Biscaye and Olsen,
'I97fa). Since material released at the Dreaged Material Disposal Site
'originates in the New York Harbor complex area, contaminants contained in
dredged material are originally introduced to the harbor water from the Hudson
'River and other tributary rivers.
Gross (1972) reported that approximately 160 km (4i/» of the harbor area)
"was covered by fine carbon-rich deposits, which were suspended solids entering
'the harbor from the Hudson River, waste discharges, and surface runoff.
TRANSPORT
MESA (1975) indicates that surface runoff of the Hudson River and the
denser saline bottom water eacn flow in opposite directions across the
Transect. In this model suspended sediments move out to sea across the
C-19
-------
Transect, then most of the material moves southward along the New Jersey
coastline of the Apex, while some moves eastward along tne Long Island
coastline of the Apex. As these solids would settle into subsurface waters,
they may return with the more saline flow into the harbor. Subsurface
currents may also move waste materials deposited in tne Bight into the harbor.
Within the Bight, suspended solids stratify during periods of seasonal sea
density stratification. A three-layer system is typically present year-round,
but is most pronounced in the spring and summer. It consists of a turbid
surface layer, a relatively clear mid-depth layer, and a turbid bottom layer.
This turbid lower layer appears to be a permanent feature of tne entire bight
•
Apex (MESA, ly75). This "nephloid layer" is thought to De a result of
agitation and resuspension of bottom sediments caused by bottom currents.
biscaye and Olson (.1976) suggest that strong seasonal thermoclines restrict
the vertical movement and settlement of suspended solids in surface waters.
While organic particles (suspended solids) containing detectable quantities of
trace metals are generally most abundant in tne bight Apex, they are
occasionally observed in upper and intermediate outer Shelf Waters. Biscaye
and Olson suggest that the most likely sources for trace metals bearing
suspended solids are sewage sludge and dredged material deposited in the Apex.
Accumulation and resuspension also affect the movement and fate of
suspended solids in the Bight. MESA (1975) reported results of sediment
sampling over the Apex. Snelf sediments are generally enriched in organic
matter and clay particles, and the Apex region lias a thin layer of ferrous
oxide (Fe O.J. Comparing autumnal suspended-solid concentrations with samples
after a November storm showed that resuspending bottom sediments resulted in a
suspended-solid concentration equivalent to 12 days of sewage sludge dumping.
In deeper areas (e.g., the Hudson Channel), muds accumulate due to reduced
bottom turbulence. Tnese muds are invariably rich in organic matter (MESA,
1975; with measurable amounts of trace metals (Biscaye and Olsen, 1976).
C-2U
-------
TRACE METALS
Trace metals occur naturally in the marine environment; nowever, most
metals exist only in minute quantities and accumulate slowly in sediments over
long periods. The population density and industrialization of the coastal
areas of the New York Bight have caused accelerated introduction of trace
metals into the Bight. Tnere are four sources of trace metals into tue bight
Apex: (i) New York Harbor (the Transect ZoneJ, (2) ocean dumping, U>
atmospheric fallout, and (4) runoff from Long Island. Metal sources can be
estimated from data by Mueller et al. Uy7b> and Duce et al. Ub»7o;. Table
C-l lists these sources and estimated average daily mass loads. Figure C-i
graphically shows the relative importance of each source.
BACKGROUND INFORMATION
Metals may be found in a number of chemical lorms. i'ae chemical form of
hazardous trace metals is important since tnis determines tne metal's
bioavailability ana toxicity. Metals can be simple or complex inorganic
species, metallo-organic complexes, inorganic and organic colloids ana
'macro-solid particles, whicn differ in chemical and biological sorptive
properties. Unfortunately, these reactions are poorly understood (Segar and
Cantello, ly?6>. however, organic complexing reduces tne biological
' availability of many trace metals (Jenne and Luoma, 1977>.
Once metals have been deposited in the sediment, several possible migration
'mechanisms between the sediment-water interface may occur: bio-oxidation,
sorption, dissolution, precipitation, coniplexation, and diffusion. Iron is
released under reducing conditions, and cadmium, copper, lead and zinc are
precipitated under reducing conditions. in tne oxidizing environment of the
Bight, the opposite reactions occur.
Seven metals; cadmium, chromium, copper, iron, lead, mercury and zinc, are
either highly toxic or highly concentrated in acid wastes (Appendix D).
C-21
-------
Cadmium has no known biological function, but acute and cnronic toxic
effects nave been demonstrated. It exists in solution as a free ion and in
complex form (Sarsfield and Marcy, 1977.) . The redox potential (En) of the
environment significantly influences the availability of the metal. In
oxidizing environments, cadmium is generally found as a carbonate, and its
toxicity to three marine decapod crustaceans ranged between J20 yg/1 to 42U
yg/1 (EPA, 1976). Reducing environments generally contain a low solubility
cadmium sulfate form ILu and Cnen, 1977).
Chromium is an essential trace element for many living organisms, and is
usually present in the reduced hydroxide state. Jenne and Luoma (1977)
reported tnat certain organic chromium compounds may increase the metal's
bioavailability by forming more kinetically active species ot tne metal.
Toxic susceptibilities of different animals are Highly variable: extremes ot
1.0 rag/1 (the polychaete Nereis virens) to 200 mg/1 (the mummichog, Fundulus
heteroclitus) nave been observed (EPA, i97t>) . hexavalent cnromium is more
toxic tnan trivalent chromium; EsPA (1975) recommends a maximum concentration
p'
of 0.10 mg/1 in marine water.
Copper is important biologically because it is essential tor synthesizing
chlorophyll; it is required in animal metabolism, and is the respiratory
pigment used for oxygen transport in some invertebrates. Organic complexing
and precipitation decrease copper toxicity (EPA, 1976). At high concen-
trations (50 to 100 ug/1), photosynthesis is inhibited and marine animals are
acutely affected.
Iron is the fourtn most abundant element in the Earth's crust, and is
required by plants and animals in all habitats (EPA, 1976). In hemoglobin, it
is the oxygen transport pigment in the blood ot all vertebrates and some
invertebrates. In marine environments, iron rapidly forms a floe which may
coat gills of fish or invertebrates, and bury or smother eggs (EPA, 1976).
Kinniburgh et al. (1977), and Krauskopf (1952) showed that iron hydroxide
significantly other metals, e.g., copper, zinc, and lead. Zinc and cadmium
are adsorbed more strongly on iron gels as pH increases.
C-22
-------
Lead has no known beneficial biological function. It is a toxic metal
which accumulates in the tissues of organisms (.EPA, 1976). The toxicity of
lead in an aqueous environment depends upon pH, organic materials, and otner
metals. Low ph increases its solubility, whereas organic or inorganic
complexing changes its bioavailabilty. Toxicity in sea water is not well
known, but concentrations of 100 to 200 yg/1 caused severe abnormalities in
the oyster Crassostrea virginica (Pringle et al., 196a;.
Mercury has no known biological function, and several forms, from elemental
to inorganic and organic compounds, occur in nature (EPA, 1976). The most
toxic form is metnyl mercury accumulated in animals, which can threaten
Uumans. Jenne ana Luoma (1977) reported that organic complexing witl
naturally occurring materials in the marine environment reduces the potential
toxicity of mercury.
Zinc is an essential element for all living organisms (Berry. 1977).
Excessive levels cause either acute or chronic toxic responses in marine
organisms. Acutely toxic concentrations in fish may cause gill breakdowns,
and chronic concentrations may inhibit growth ana maturation in juvenile fish,
or cause general lethargy and histological damage to mature individuals (EPA,
Iy7b). Zinc toxicity is reduced by complexing with organic materials.
SOURCE INPUTS
Table C-l lists trace metals from the four primary sources. Ocean waste
disposal (excluding acid wastes) is the most significant contributor of metals
except lead and zinc.
Dredged material (Table C-6) is the largest source of cadmium, copper,
chromium, and iron; dredged material and sewage sludge contain approximately
equal quantities of mercury.
Sewage sludge is the second largest source of trace metals (see Table C-6;
and contributes about 50% of the daily input of mercury, with ctiromium (24;»; ,
lead (13%) and zinc (20%) also high.
C-23
-------
Inputs from the Cellar Dirt Site have not been estimated, but are probably
insignificant sources of trace metals (Interstate Electronics Corp., 197c>).
Passing through the Transect Zone is contaminated water and surface runoff
from New York. Harbor and Raritan bay estuary (.Table C-l). Many contaminants
entering the harbor settle in quiet water areas and remain trapped in bottom
sediments. They may be introduced into the iiight after dredging and released
at the Dredged Material Site. The Transect Zone contributes the largest
volume of wastewater, with the largest average daily quantities of Lead (4//0;,
zinc (53/.), and the second largest quantities of cadmium U5/i) , chromium
(4Z/O, copper (47/i) and iron (16/i).
The Long Island coastline contrioutes only very small quantities of trace
metals to the Apex. Of the seven metals examined, the Long Island coastline
contributes less than one percent of the daily total in all cases.
IRON
Redfield and toalford (1951) examined iron accumulation in waste discharges
at Raritan Bay and the Apex. The iron concentration at the moutn of the Lower
Bay was four to six times that of the offshore water concentrations. Tnese
high concentrations were associated with low salinity surface outflows from
the Lower Bay. In 1951, the Raritan River contributed approximately 45
tonnes/day of iron to the Apex. It was estimated that an equal quantity of
iron (.45 tonnes/day) was disposed at the "acid grounds".
Segar and Cantillo (.1976) reported that most iron is associated with
suspended sediments in the lower New York Bay with maximal concentrations
occurring just after maximum ebb tide (MESA, 1975). This implies that a
significant "pool" of particulate iron exists within the harbor complex. The
bulk of this iron is precipitated or dispersed within a snort period upon
entering the Bight. In addition, Segar and Cantillo (1976) reported a widely
distributed nephloid layer containing a high concentration of fine particulate
matter, including iron, at the sediment-water interface within the Apex.
C-24
-------
New York Harbor sediments show iron as l.d/. of the total dry weight.
Samples from the Dredged Material and Sewage Sludge Sites averaged about 1.05-i
of the total dried sediment weight, which was not greatly different (Gross,
1970).
It is not possible to estimate the iron concentrations at each disposal
site, since dredged material and sewage sludge are not analyzed tor iron
concentrations. In 1977, ML Industries began reporting iron concentrations in
its waste. based on these values and the volumes discharged, Table C-tf shows
the approximate amounts of iron released by ML Industries compared to other
inputs. Initially, ML Industries contributed about three quarters of the
total input of iron. In more recent years, their contribution has decreased
to two thirds of tne total (Appendix D).
TABLE C-8. AMOUNTS OF IRON RELEASED INTO THE NEW YORK BIGHT
(Tonnes/Day)
NL industries
4
Other Sources
Total
Percent NL
Industries
1973
182.2
51. 0
233.2
16
1974
157.1
51. U
208.1
75
1975
145.6
51. U
1*6.6
74
1*76
111.9
51.0
162.9
b9
19771
62.5
51.0
113.5
55
19782
100.5
51.0
151.5
bb
Sources:
1 Calculated only for the montns NL Industries released waste
at the Acid Waste Site.
2 Estimated from eight months of data
3 Data from EPA Region II files
4 Data from Mueller et at., 197b. Sources include tue
Transect Zone, atmospheric fallout, and the New Jersey ana
Long Island coastlines.
C-25
-------
OTHER TRACE METALS
Toxic trace metals have been examined by numerous researchers. within the
narbor waters, MESA (.1975) reported that cadmium, lead, and mercury were below
detection limits in waters of the Transect Zone. Particulate and soluble
copper varied with the tide and sampling location. Copper was primarily in
the soluble form. Alexander and Alexander U977) reported that particulate
lead and cadmium were always less than 0.5 ug/1 and U.I yg/1, respectively.
begar and Cantillo (1976)'examined trace metals in Apex waters. Copper and
cadmium were uniformly distributed during spring, except for isolated areas of
increased concentration.
Discharge from New York Harbor contains low concentrations of cadmium and
copper. During summer, copper concentrations remain uniform, between 2 ug/1
to 4 yg/1. Levels north of the Acid Site were usually higher than other
regions of the Apex. Cadmium concentrations over the Apex varied slightly but
estuarine and near-bottom samples contained higher concentrations of these
metals.
Segar and Cantillo (1976) concluded that summer and mid-winter metal
concentrations were higher than spring and autumnal concentrations. During
summer, the water column is stratified and restricted circulation increases
the water's residence time which leads to Higher equilibrium constants. In
winter, current and wave energy increase sediment movements, thus releasing
metals from resuspended sediments. Iron appears to be found predominantly in
the suspended phase while copper, cadmium, and zinc are found predominantly in
the dissolved phase. Therefore, copper, cadmium, and zinc are present only in
small quantities.
Gross (1976) found that high concentrations of trace metals were widely
distributed within New York Harbor sediments. Chromium concentrations were
approximately JuO g/tonne in lower harbor sediments. Copper was estimated at
20U g/tonne and lead was estimated at 700 g/tonne of sediment. In comparison,
sediment samples from the Dredged Material and Sewage Sludge Sites had
C-2o
-------
concentrations of about 150 g/tonne chromium, 90 g/tonne copper, and
150 g/tonne lead. The dredged material is an important source of contaminants
to the Apex, but the ultimate sources of these metals are the contaminated
waters flowing into New York Harbor.
Segar and Cantillo (.1976) state that much of the solid wastes dumped into
the flight Apex is rapidly dispersed and transported so that flushing of the
Apex must be an efficient process. The wastes may move seaward or possibly
back towards shore. Freeland et al., 1976, and freeland and Merrill, 1977,
however, concluded that most of the dredged material released into the Apex
remains in place. Comparing a 193b bathymetric survey with a 1973 survey,
approximately 87% of the material released at the Dredged Material Site was
still in the vicinity of the site. Earlier, Pararas-Carayannis U97J, 1975;
had reached similar conclusions. Apparently, those metals which are loosely
bound to the sediment are mobilized and quickly carried out of the Bight. Tue
remainder are tightly bound to tne sediments and hence have a low bio-
availability, but metal bioconcentration can still occur. Gross U976)
reported that deposits from the Hudson Channel south of the disposal sites
contain metal-rich sediments and that metal buila-up in bottom-dwelling
organisms may be occurring.
OIL AND GREASE
Oil and grease is a general category which includes thousands of organic
compounds. These contaminants may have either anthropogenic or natural
origins, and produce both acute and chronic toxic responses in marine
organisms (EPA, 1976). Larval and juvenile stages of marine organism life
cycles may be especially sensitive to increased levels of these contaminants.
Oil and grease are present in all contaminant sources except the atmosphere
and cellar dirt. They enter the Apex at a rate of approximately 7tfU
tonnes/day (Table C-4), constituting the second largest quantity of all
contaminants examined (Mueller et al., 1976).
C-27
-------
Mueller et al. (1^76; estimated that the Transect Zone contributed approxi-
mately 460 tonnes/aay (jJZ,). Ocean dumping contributed approximately 322
tonnes/day, of whic;i 9J/o (300 tonnes; is from dredged material, ana T/a (22
tonnes^ trom sewage sludge::. Tne Long Island coastline contributes only about
0.7 tonnes/day, less tnan 1/i of the daily total.
Examinations of the sources of oil and grease indicate that tney are
entirely of anthropogenic origin. Within the Transect Zone (Table C-5J two
primary sources of oil and grease can be identified: (.1) municipal and
industrial wastewaters, and (.2) urban discnarge. Each contributes about 200
metric tons/day to the harbor area. By comparison, dredged material (Table
C-b) contributes an average of 300 tonnes/day, indicating that much of the oil
and grease reaching the harbor is trapped and retained in harbor sediments,
and later removed by dredging activity. Coastal discharges (Tables C~2 and
C-3) are from municipal and industrial wastes and surface runoff. DJew Jersey,
which is highly industrialized, discharges about 75 tonnes/day along its
coast. Presumably, little of this contamination ever reaches the apex region
because of prevailing currents moving southerly along the coast. About 90/o of
the oil and grease from New Jersey is from surface runoff. Tne remaining 10/i
is from municipal and industrial wastewater. Long Island, which is much less
industrialized, discharges only about 5 tonnes of oil and grease per day, and
of this only about 15% (0.7 tonnes) enters the Apex. About yO/» of the Long
Island discharge is from municipal and industrial waste water. Tne remaining
10/i is from surface runoff.
-------
Appendix D
CONTAMINANT INPUTS
TO THE ACID DISPOSAL SITE
-------
CONTENTS
PERMITS AND WASTE VOLUMES D-l
Years 1973 to 1978 . D-l
Projected Inputs D-3
WASTE COMPONENTS D-4
NL Industries D-4
Allied Chemical Corporation D-12
Du Pont-Grasselli D-16
COMPARISON OF CONTAMINANT INPUTS D-l7
Figure D-l Reported Dumping Volumes at New York
Acid Dump Site D-3
TABLES
D-l Disposal Quantities (Tonne/Year) D-2
D-2 Waste Characteristics D-7
D-3 Waste Constituents - Allied Chemical D-14
D-4 Mass Loading - New York Bight Apex (Tonne/Day) D-l 7
D-i
-------
Appendix D
CONTAMINANT INPUTS TO THE ACID WASTE DISPOSAL SITE
PERMITS AND WASTE VOLUMES
YEARS 1973 TO 1978
When tne Acid Site ca.ne under EPA regulation in 1973, three Mew Jersey
companies (Du Pont-Grasselli in Linden, Allied Chemical in Eiizabetn, and NL
Industries in Sayreville) , were using tne si|;e for Disposal purposes. In
1974, ttu Pont-Grasselli moved its entire waste disposal operation to the
10b-Mile Chemical Waste bite, as required l?y EPA. In iy79 only Allied
Chemical and NL Industries are disposing of wastes at the Acid bite.
Records of NL Industries' waste disposal activities have been maintained
since the late 1950's. However, when the EPA began regulating and monitoring
ocean flisposell activities in 1973, more detailed analyses were required. NL
Industries disposes of waste on a daily basis, occasionally barging wastes
twice a c)ay to the site.
NL Industries is the largest waste contributor to the Acid bite in terms of
amount of waste. Annual quantities (Table D-l) fluctuated considerably
between 1973 and 1978, although the long-term average from 1956 is fairly
stable (Figure £M). This recent fluctuation resulted from a plant shutdown
in mid~1976 and start-up again in mid-1977. For approximately nine months,
all plant production was halted. The mean annual quantity of waste material
dumped between 1973 to 1978, has been 1.8 million tonnes, ranging from 0.605
thousand tonnes in 1977 to 2.3 million t'onnes in 1973. Since 1958, NL
Industries has contributed over 90% of the total vplume of waste material
dumped at the Acid Site.
D-l
-------
TABLE D-l. DISPOSAL QUANTITIES (TONNES/YEAR)
NL Industrie
% Contribution
Allied Chptnical
% Cont ri but i on
Du Pont-
Gra^plli
/o Con tr i but i on
101 A LS
1973
2,304,250
92.0
58,967
2.3
142, 42b
5.7
2,505,645
1974
1,986,735
93.5
56,245
2.6
76, Ol» •
3.7
2,120,990
1975
1,841,586
97.5
•' "ib.dbl .
2.5
—
1 ,889,667
1976
1,233,722
96.5
47,174
3.6
1,280,946
1977
604,733
95.4
29,030
4.0
—
633,763
1978
1,233,792
97.9
26,259
2.1
1,260, 101
' 'TOTAL
9,204,868
265,806
220,446
9,691,120
Records of Allied Chemical waste disposal activities have been maintained
since the EPA began regulating and monitoring waste disposal at the Acid Site
in mid-1973. Since 1973, Allied Chemical has disposed of approximately
255,000 tonnes of waste .material, averaging about 50,900 tonnes/year (.ciata
from 1973 to 1978).
Allied Chemical's waste.s are .less than 5% of all waste material released at
the Acid Site. Unlike NL Industries, Allied Chemical disposes of waste
material intermittently, only once or twice a month. Tne total volume of
Allied waste barged to the Acid Site has dropped 55% since 1973.
Du Pont-Grasselli discontinued disposal activity at the Acid bite 1974. At
that time, they shifted their entire disposal operations to the 106-Mile
Chemical Waste Site. During 1973-74 in which Du Pont dumped at the Acia Site,
they disposed of approximately 220,000 tonnes of waste material, or about 5%
of the annual input.
D-2
-------
4.5-
4.0-
, 3.5 -
LU
| 3.0 H
u
§ 2.5 H
U
0 2.0 -
i/»
z
0 1.5-
i 1.0 -
0.5 -
I •' l
1960
V
1958
T 1 T
1962
1964
T 1 1 T-
1966 1968
~T 1 1"
1970 1972
1 1 1 1
1974 1976
Figure D-\, Reported Dumping Volumes at New York Acid Dump Site
(Adapted from EPA, 1978a)
PROJEqTED INPUTS
WL Industries' permit wnich expires i April 19rfl allows them to dispose or
2.7 million tonnes ot aciu wastes during the 2-year permit terra, or about 1.4
million tonnes per year. Inis is lower than tne previous 5-year average
(l.rf million tonnes). The maximum amount permitted in 1 year under tnis
permit is 2.3 million tonnes, which is about equal to the long-term average ot
2.2 million tonnes.
Allied' Chemical ' s permit wnicri expires y April' lyoi, allows them to dispose
of 32,UUO tgnnes of acid wastes per year, which is about equal to the previous
5 year average annual input, (53,000 tonnes). However, Allied Cneuiical
anticipates that 1979 discnarge volumes will be about tne same as tne I97d
volume (26,000 tonnes) wnicn is about nalt ot the permitted amount (titts,
1979).
D-J
-------
Consequently, the two permittees are authorised tp release approximately
1.4 million tonnes per year, which is 27/b less tnan the previous 5-year
average.
WASTE COMPONENTS
Each barge sample analysis (for the Acid Site) since 1973 has been reviewed
to estimate the total constituent loading. Interstate Electronics Corporation
has developed an automated data handling and analysis system; the Oceano-
graphic Data Environmental ^valuation Program (ODEiiP). OuEEi' was utilized to
evaluate the wastes dumped at the Acid bite. The results ot trie analyses ol
iNL Industries and Allied Chemical's wastes are presented in tins section.
Only yearly means and ranges are presented. There were no significant
differences in waste characteristics during different seasons; consequently,
the yearly values adequately represent what was aumped at the site.
Approximately !i,t>00 data points were used tor these analyses. tonen evaluating
this loading, two factors are important:
• The liquid waste does not appear to affect the bottom, .
• Tne waste is neutralized rapidly (,in minutes; and environmental
effects have been associated only with unneutralized waste,
b'ince waste constituents do not accumulate in the water column, tne
material does not remain at the site but is carried out ot tne bignt. Tne
amounts per day of waste constituents are most relevant since these represent
roughly the inputs from a single barge load.
NL INDUSTRIES
ML Industries disposes ot wastes produced in tne manufacture of titanium
dioxide, an inert, nontoxic white pigment used, in papep, pej.nt, plastic,
drugs, and ceramics. Waste material consists oi approximately 10.U/!> (by
weight) ferrous sulfate (FeSO^), 8.57o (.by weight) sulfuric acid tH^SU, ) , and
1.5 - 2.0 g/1 titanium. Other trace metals, and oil and grease are present in
minute quantities.
D-4
-------
The waste is released below the surface of the water through 30-cm diameter
pipes in the wake of a barge. The barge is moving at 5 to t> kn. Tne maximum
permissible disposal rate is 376,QUO liters UUO,UOO gal; per nmi. Using this
discharge rate, an average Darge load of 3.7 million liters of waste can be
released in approximately 90 minutes, over a distance of about 9 nmi. As the
waste is released into tne seawater, tne acid is neutralized, and the ferrous
sulfate stains the water a characteristic green color. Tne terrous iron is
rapidly oxidized to ferric hydroxide (rust; and this gives the water a
"muddy," red-brown color.
PHYSICAL CHARACTERISTICS
Specific gravity of ML Industries waste has, with one exception, ranged
between 1.082 and 1.197 (.a single value of 1.425 was reported in August Iy7o>.
The average specific gravity is 1.132. These densities are greater than
seawater (1.1)25; so the waste sinks and disperses through the water column
during periods of homogeneous water column density (winter;. During summer
months, when distinct thermocline and pycnocline stratifications occur,
sinking and dispersion are restricted to the upper mixed layer, which is
typically 10 to 13 m in depth. :
The speed of the mixing of waste with seawater is a function of prevailing
meteorological and oceanographic conditions. Following discharge from tne
barge, initial mixing occurs rapidly (within tne first 15 minutes) primarily
as a result of barge generated turbulence. After this period, wind, waves,
currents, and density stratification determine the rate and direction ol
dispersion and dilution. The most recent dispersion study of NL Industries
waste was performed by EG&G (1977a) in August 1*77. Waste material sank to a
depth of 10 m and rapidly dispersed laterally under conditions of nigh winds
and moderate seas.
EGiiG (1977a.) recorded seawater iron concentrations and ph values to track
the waste plume. They determined that a concentration of 2 yg/1 (acid-waste;
of seawater was equivalent to the ambient seawater iron level and a value of
5 yg/1 indicated the presence of the waste plume. before the disposal
D-5
-------
operation, iron concentrations in the upper roiftgtt layer and below the
thermocline were measured at reference stations 7 The m,§a,n. iron concentration
of upper mixed layer water was 0,05 uj>/ 1 and t;}ie mean iron concentration of
subsurface layer water was 0.02 US/I- Immediately £pllQvi^ s|?rscha.rge, the
surface iron concentration was 2:3,30,0 rog/ 1 . This fspnce^tr^tipn. dropped
rapidly ana 14 minutes after discharge the maximum surface iron concentration
was 1.9 rag/ 1 .
by monitoring iron concentration , the
Forty minutes after discharge, the wast;e wa,s
f
hours the minimum wa.ate dilution w#s 90,000:1, a.
showed a minimal dilution of lib, 0,0,0. !l.
can be determined.
to 9,,400!i. After tour
a.fctep 1$ hours one station
Federal environmental standards reqvtfr§ thaf
ambient pH level more than 0.2 pH units beyond a
(.EPA, 1976;. The £G6 anu 3$
within the normal pH range foi^ this are.fl of
1974).
do not change tne
limits of o.i to rf.3
wj.th a pH change
ambient value. In
reduced U.-O any J , 21 ph
value pt ,^f2. iaese
qiscaargtj anu were well
CO ti.2 (hazelworta et al.,
CHKH1LAL CHAKACTEKlSi'iCS
Table D-2 sunnuar^^ep the charapRer istics of yar^OMS waste constituent? and
the inputs into the Bight Apex. For convenient^, the tot;al input from ail
sources of each constituent are shown t'oy comparison, obviously, the
contaminants present in NL Industries waste are trivial (^^) sources of total
contaminant loading in tne bignt, gowwents at»9Mt: specific waste character-
istics follow.
The extremly low pH of NL Industries' w^StJf is rapidly neutralizea by the
buffering action of sea water. The timq £o reestablish jUTibient pn values has
-------
TABLE D-2. WASTE CHARACTERISTICS - NL INDUSTRIES
Chemical
Parameters
Soli do (ug/ 1)
Organic*
hydrocarbon1*
Caonii urn
Chromium
Copper
Lean
Ni'rcury
L\ nc
Kange
(ug/1)
2.0 20,50u
1*0 - 50,600
2uO 4b,200
lu 500
2,uou Ib.Wu
12J 140,200
27u bb'O
0.5 B
45U jb.luO
Mean
3,760
5,440
4,b50
200
10,*UU
4.1UO-
I,b70
4.7
20->0
Avoragp "u>arly
Input
( tonnes )
2.S60
6.0
3.7
0.3
14.2
4.S
2. 1
0.005
2b.4
Av.Tiigp La i ly
Input
( tonnes/ day)
12.6
0.02
0.01
0.01
O.U4
o.ul
O.ul
U.01
O.u7
Averagf Lv i Ly
inpu l-othor sources
( t iinnes/ uay )
2j,5bO
7b3
no data
2.43
5.2fa
13.2
12.4
u.52
32.1
Percent
Acid Waste
input
u. u5
O.OU
d.OJ
U . o
O.Ub
u. LtJ
u.Ul
0.2
Physical
Parameters
b[.'i?c i ii c oravi t y
1.0b2- 1.11,7
O.lo l.u*
1. 132
ranged from minutes (.Redfield ana Walford, 1^51; to 2.3 hours (,EGu.G, i977a;.
Ambient ph levels are never depressed outside the site's boundaries during the
4-hour perioa oi initial mixing (ERGO, iy?8aj . The extremely low ph values
which cause harmful effects to the plankton are present tor only a oriel
perioa (less than thirty seconds; Realiela i* kvalforu, 1951), ana only around
the barge's discharge port.
Suspended Sol ids
Some inert materials, gangue and uncombined titanium ore, are present in
the waste, ati<3 these are suspended solias reported in Table D-2. The iron
floe wnicn forms after waste release is not part of these values. However,
even with this additional suspended material, there is no danger that waste
constituents could reach the snoreline in measureable amounts. ERGO (1^76aJ
calculated that minimum dilution of the waste, it it moved in a straight line
directly to the beach, would be two million to one. The concentration of
iron tne most abundant waste component, would be about naif of the normal,
ambient value.
-------
Trace Metals
Four metals (.arsenic, nickel, titanium and iron), in Addition to the six in
Table D-2, are measured in NL Industries' waste. Although tpftic, arseni,c
forms compounds after release and the organo-metallic complexes do not appear
to accumulate in the food chain, and are not highly toxic (EPA, 1976), This
conclusion is supported by bioassay results which have shown low toxicity in
neutralized acid wastes (see Bioassay Section). Nickel, titanium, and iron in
these amounts are considered to be nontoxic to man (EPA, 1976).
Titanium and iron are present in high concentrations in NL Industries'
waste; 1.9 g/1 and 27.6 g/1 respectively. Daily inputs average tf.6 and 148
tonnes/day and represent a major source of these metals at the Apex. Field
observations and bioassay results have shown no adverse effects on the
plankton from these metals (Appendix B) .
TOXICITY
As outlined above, waste from NL Industries is an insignificant source o£
contaminants to the Apex of the New York bight. Iron and titanium, which are
significant inputs, are nontoxic. However, the waste is released in a small
area over a short time and localized effects may occur in the site region.
Therefore, the EPA requires bioassays and field studies to evaluate the
toxicity of the wastes. This work has demonstrated that wastes are toxic only
for a few minutes after discharge; long-term, chronic effects have not been
observed.
Bioassays
Bioassays of NL Industries' wastes must include analyses qt the Affects of
various waste concentrations upon organisms indigenous to the Disposal site.
Bioassays are now conducted under procedures required by Federal standards
CEPA, 1978b).
D-8
-------
Bioassays nave been performed upon waste samples since the permit program
started. Representative species in tnese studies include the phytopiankters,
Skeletonema costatum, and fish Menidia menidia. Artemia saiina (an estuarine
copepod) was used extensively in the past, out tae latest bioassay standards
require the use of more representative marine organisms.
Phytoplankton test organisms are to be examined tor the effective
concentration (.EC^) which causes a 50/o reduction in cell numbers (^compared to
a control group; after 4b or 96 hours. Zooplankton and nekton are examined
for the lethal concentration (LC J at which j>J/o of the test organisms die
after 46 or y& nours.
Results of bioassay tests, conducted since ly/J, show that the toxicity to
Artemia saiina varies between LC,-. values ot 100,000 mg/1 to i,i:o mg/ 1.
Variations are due primarily to changes in the Federal mandates tor tests
(.before 1977, unneutralized wastes were used; and test organisms, but not
because of radical changes in the toxicities ol tne material. lue annual mean
LC.-.. values for bioassays ranged trom 92.4 mg/i to 302 mg/ i in non-aerated,
9o-hour tests. Simultaneous bioassays on _M. menidia in yo-hour, aerated
tests, had mean LCc values of 101 mg/1 (.1977) and 2t>2 mg/1 (1176). iiioassays
on Skeletonema costatum had mean 96-hour LCc,) values of 174 mg/1 Uy/o;, 241
mg/1 (.1977) and 106 mg/1 (I97d,).
Tests demonstrate that waste materials dispersed by iSL Industries will De
acutely toxic to planktonic organisms for only a tew minutes. Ihe dilution ot
waste occurring immediately after discharge reduces concentrations to values
below the levels known to be toxic to representative organisms. The
concentration of iron, the most abundant waste contaminant, was i.y mg/ 1
fourteen minutes after discharge (EGi*G, 1977 a;. These tests do not, however,
evaluate chronic effects which may impair reproductive or benaviorai aspects
of species at the individual or population levels. Field observations (see
below) confirm the low toxicity of waste in the Darge wake.
Field Studies
The first biological observations of effects due to acid waste disposal
(Redfield and Walfora, 1951), snowed that fish or benthic populations were not
-------
being damaged or excluded from the area. ftpppla^k^pn entrained in qpntami,-
nated wake water were temporarily immobilized but reeo/vered wnen the
contaminated water was diluted, which occurs rapidly in the, b,a,rpe, wake,
Ketchum et al . (1958.) reported that plankton tfpws, taken shortly alter
acid-iron waste disposal, were clogged by .fiogculent iron precipitate ranging
from 5 to 70 microns in diameter. 2,ooplan,kto,n Iwhich normally feed on
phytopiankton about this size) captured in the wake did contain large
quantities of "brownish material" which was "presumably tfte iron precipitate."
The zoopiankton appeared nprmal and it was, stated that the "studies have
failed to demonstrate any deleterious effect pf, this w,aste disposal on the
plankton populations of tne area,"
The most recent comprehensive study of the ^fleets of apid™iron waptes is
reported by Vaccaro et al. Uy"/2J, A waste, concentration four times greater
than values observed in the field produced no ^gv££S3 effect on phytopi&nKton
growth or diversity. Only the zooplankt°P snowed chronic effects. Alter
eighteen days of exposure, reproduction an,q ^rqwfth were affected by a
concentration of 1:10, OUO waste, showing a "failure of the organf^ms
1 zpopianktonj to reproduce, or a delay in the tiifle required to transtonn eggs
into adults." These results, however, are not; b,i t?enlfhps, and sediments
examined. Concentrations in the Acid Site area were, signilfciftntly higher than
in the control area. However, samples from th$ jtiudSPR Va«yo.h ^ad the highest
assimilations of lead and chromium in bent}1!©.? f»Wd ^? iTHi-ghes); aiwu,ht;s, pi all
eight metals in sediments, suggesting th^t canyRif sedime(nt^ »Tiay pe the area of
greatest heavy metal enrichment. The confrql a?ea was located outside of the
Apex, thus the results may only show that, in general, mqtal concentratJ-pns
inside the Apex are higher than those outside.
-------
Grice et al. (1973) concluded that short-term effects of acid waste
disposal are due to short-term acidity fluctuations rather than toxic
components of waste material. Mortality during short-term exposure to high
concentrations of the waste material is small; it is notable that adults and
larvae are not appreciably affected by heavy concentrations. It was noted
that reproductive inhibition of adults and reduced survival of young copepods
occurred only after 18 days of exposure. The pH was held below 6.5, but these
levels occur for only minutes after actual discharges. No mortality was
observed when the animals were passed through acid waste dilutions at pH
levels ana periods comparable to barge dumps. Gibson (1973) confirmed earlier
experiments that the acididy of the waste is the toxic factor. Animals heia
in neutralized ac'.d waste showed no mortality, whereas others kept in sulfuric
acid solutions, simulating acid waste, showed high mortality at pH levels less
than 5.5.
Some work on biological assimilation of trace metals was performed at the
former Du Pont-Edgemoor Industrial Waste Site. Until 1978, Du Font-Edge Moor
discharged an acid-iron waste at this site similar to wastes released by NL
Industries. Pesch et al. (1977) investigated trace metals in scallops at two
disposal sites: the industrial waste and municipal sewage sludge sites. The
input of four metals (iron, manganese, vanadium, and titanium) were due to the
acid wastes, not the sewage sludge. Consequently, these four metals can be
used as tracers of acid waste accumulations in an area which is isolated from
other anthropogenic pollutant sources. Pesch et al. (1977) found an area of
high vanadium concentrations in scallops south of the site, in the direction
of projected plume transport. Examinations of the other three metals,
however, did not follow the same trends; when all four metals were considered,
"high" stations existed to the south and north of the site, occasionally near
a "Idw" station. The findings, although indicating possible effects of
acid-iron waste upon benthic organisms, require more confirmatory evidence.
In the New York Bight such effects would not be observable because of the high
inputs of contaminants from other sources.
D-ll
-------
ALLIED CHEMICAL CORPORATION
Allied Cnemical Corporation disposes of wastes resulting from the
manufacture of refrigerants. waste materials consist of approximately JiU
(weignt) hydrochloric acid, 2 X, (weignt) hydrofluoric acid, and trace
constituents in aqueous solution. Trace metals ana oil and grease are present
in minute quantities.
Wastes are released below the ocean surface through 30 cm oiameter pipes
into the wake of a barge moving at 5 to b knots. The maximum permissible
uisposal rate is 45,400 liters (12,000 gaU per nmi. Therefore an average
waste loaa of 1.6 million liters can be e,mptiea in approximately six hours,
over a distance of about 35 nmi. Allied Chemical's w^ste does not discolor
cue receiving water.
PHYSICAL CHARACTERISTICS
Specific gravity (density.) of Allied Chemical waste, with two exemptions,
has ranged between 1.116 and 1.200 (.values of 1,57 ana 1.6U were reported
March and April 1^76). Tne mean value is 1.170 wuiQh is greater tzftan seawate.r
(1.025;; thus waste sinks and disperses thrpwgh f,he water cpiumn quring
periods of homogeneous water column density. J.n sunimer months, when
thermoeline and pycnocline stratifications occur, sipking and dispersipn are
restricted to tne upper mixed layer stratum, usually about 10 tp 13 m deep.
Dispersion studies of Allied Chemical wast$ W^re cqnducted Dy
Environmental Consultants (EG&G, lV77b), Waste [jiateri^l, sank rapidly to the
bottom of the surface mixed layer and remained there,. After several nours , no
significant penetration of the thermociine was observed. Tne wastes were
tracked by monitoring dye concentration and pH cnanges.
Waste concentration diminished uniformly witn tfepth during tne first few
Vtours of dispersion. The maximum waste concentration was 3faO rag/ 1 one minute
after discharge, and about 36 mg/ 1 45 minutes later. After about two nours,
/ertical waste distribution began to exhibit patchinesg, with localized areas
of nigh concentrations above tne thermociine and near the surface. After
U-12
-------
three hovjrs , maximum concentrations were found near the tnermocline. Four
hours after discharge, maximal waste concentration was 18 mg/ 1 at 5 m.
One minute after discharge, the dilution ratio was approximately 2,700:1,
increasing to 15,000:1 in four minutes. Tnree hours after discharge, the
dilution ratio was 83,000:1, and 143,000:1 after four hours.
Current shear was a noticeable factor in waste dispersion. Tne upper 10 m
(mixed layer) appeared to move eastward relative to the subsurface core at
10 m. The entire plume moved_with tidal currents approximately 2 ntui (J.b kiiU
west of the original position.
Marine water quality criteria specify triat ph must be maintained between
6.5 and 8,5, and may not be affected by more than jHJ.2 ph units. Ambient ph
values decreased 0.7 units immediately after discharge, but, as natural
neutralizing and dilution continued, the ptt within the plume steadily returned
to ambient values. Four hours after discharge, pH values had returned to
within 0.2 pH units of normal ambient levels.
CHaMlCAL CHARACTERISTICS
Table D-3 summarizes characteristics of various waste constituents ana
inputs to the Bight Apex. Inputs from all sources are shown tor comparisons.
Obviously, the contaminants present in Allied Cnemical1 s waste are trivial
sources (<0,01%) of total contaminant loading in the Bight. Comments about
specific waste characteristics follow.
The extremely low ph of Allied Chemical's waste is neutralized by seawater
buffering aqtion well within tne four-hour period of initial mixing mandated
by the Ocean Dumping Regulations. The initial pH vaLue is 7.5 after waste
release (EG&G, 1977 b) , which is 0.7 units less than ambient values and lower
than the normal ph range of the site. Tne pH values rapidly return to ambient
levels. Minimal pH's after initial mixing were: 8.07 at 1 m; 7.90 at 5 m; and
8.03 at 10 m. Normal ambient pH range for this area is 7.9 to 8.2 (.hazelwortn
et al., 1974).
-------
TABLE D-3. WASTE CONSTITUENTS - ALLIED CHEMICAL
Chemical
Parameters
busppnded
Sol ias
u i 1 & Grpfise
Ppt roleum
Hyarocarb )ns
Cadroi urn
Chrom i urn
Copper
Lrad
Hrrcury
ii nc
Range
(ug/1)
JO 246 mg /I
1UO 20,000
100 13,000
2 200
10 3,040
10 2,400
lu 4BO
0.02 170
2 1,200
Mp.an
(ug/1)
25 mg/1
4,450
l,56o
l(f
IV*
124
102
12.5
156
Average Yearly .
Input
( tonne-0
0,7
0,2
0.07
0.01
0.04
0.03
U.U2
0.01
0. OJ
Input per
barge *
( tonnes )
1,1,00
0,02
U.01
g.oi
U.ul
0.01
o.ol
0.01
0,01
I'lrll /,'IU f"Tii 1."" TFT? ' "1"' 1> "
iVvfjrage Dqily
Inpptrofnfir sources
( ti^nnep )
2^,560
7W
no qata
2.4
5.3
13.2
iirt
w.5
32.1
Ml'lllll'l.ni),, |l )l !M;;| r-r-
^oifl ffUfif
IPPHf (i.)
O.UJ
0.01
U.Oi
o.ol
0.01
0.01
O.Ol
0.01
Physical
Parameters
Speci fie
Uravi t y
ph
1,116 1.200
0.10 2.20
1. 170
12 bargrs/year
Suspended Solids
Allied Ciiemical waste does not contain insplu&le materials, ana does not
react with seawater to form precipitates, 1'here is nq danger ot
constituents reaching the shoreline in measurable amounts. EKUQ (
calculated that minimum dilution of the waste, traveling straigntiy and
directly to the beach, would be one million to pne, The concentration of
fluoride, the most abundant waste component, would be about 2/k of the normal
ambient value.
Trace Metals
Two metals, arsenic and nickel in addition to the six in Ta,t>le p-^ , are
measured in Allied Chemical's waste. Comments qppHefl to Nt, Industries'
wastes are equally applicable to those from AH ^e<4 . ?he n0nERCQ,
-------
TOXIC IT *
Bioassays
Alliea Chemical aoes not aispose ot waste daily, unlike iNL Inaustries;
Allied Cnemical introduces waste in a pulsate manner. Wastes may accumulate
for several we,eks, and are barged to the site once or twice per month.
Kea tie Id ana toalford Uypl) concluded that total flushing of the entire Apex
takes from a to 14 days. Therefore, Allied Cnemical waste is extensively
diluted and, in ail probability, flushed from the Apex before any subsequent
disposal occurs, thus eliminating the potential for compounds to accumulate in
sediments or biota of the Apex.
Results of bioassay tests show annual mean •Jo nour LU- . values in Artemia
j \j
salina (copepou) ranging from 52,a_ij mg/1 to 97,42^ mg/1. Similarly, 4cS hour
LCc,, yearly mean values.,for A_. salina range from 12J mg/1 to 2J3 mg/1. Trie
Differences in lethal concentrations uo not suggest extreme toxicological
effects, but are rather due to differences in test procedures.
Skeletpnema cos, t a turn (phytoplanktonj nave mean yb-hour ECr values ranging
from lOb mg/1 to J5u mg/1 with respective standard deviations of ll and
-i42 mg/ 1.
Henidia menidia (.nekton) nave annual mean TLc-, values for yo-aour aerated
samples ranging from 2U13 mg/1 to 27ii mg/1. TL^ values from 4d-nour tests
have annual mean values ranging from 2_>J mg/ 1 to 260 mg/1. Non-aerated tests
produce approximately equal TL- values for the sane waste samples.
Acartia tonsa Can estuarine copepoaj had a mean 9b-nour 1^.. value or
72 mg/1 in iy?i, and a mean yb-nour TL50 value ot 61 ing/1 in ly/o.
All tests demonstrated that waste materials disposed by Allied Chemical
have only short-term acute effects upon marine organisms. The highest waste
concentration was 3bU yg/1 one minute after discnarge, out only Jo yg/1 45
minutes after discharge. Waste dilution several minutes after discharge
reduces concentrations to values below the toxic levels of representative
-------
organisms. The tests do not, however, confirm chronic effects which may alter
or impair reproductive and behavioral aspects of species at the individual or
population levels.
Field Studies
Allied Cneraical does not dispose ol acid waste material a^ irequently as WL
Industries, nor are waste volumes as great as jflk in single disposal
operations, however, Allieu Chemical waste is more acidic, thus necessitating
a slower release into receiving waters in orcier to minj,mi?e short-term impacts
upon biqta.
Cuemic&l analyses have continued that the cpiiipps.i.ti.pns pi NL and Allied
wastes are similar t, except lor iron ana Cit^ViifM1' CQHteciU, ancj uioas,say
stuuies show similarities in toxicity. Taereiore, impacts of the two wastes
are assumed to be similar in the dump area.
DU PONT>GRASSELLI
Du Pont-Grasselli produces production wastes trpm DMhA IW,U-'dj.mefiftyl
hydroxylamineJ and Anisole. During 197J and 1974t when Pu Fqpt-rCirasseiii, was
dumping in the Acid Site, the contribution was approximately >/i pf ^h^ annual
input (Table 1>-1). Since 1973, however, all 1X1 Popt wastes ft^ve! been released
at the 106-i'iiie Chemical Waste Site.
The primary constituent of l)u Pont-Qrasseilj, waste is sotjium sulfate
(Na^SO,^, with numerous trace metals, suspended splids, and variqus organic
substances .
Specific gravity of l)u Pont waste averaged l.Udbl, slightly greater than sea
water, but less than ML Industries and Allied Chemical wastes.
Du Pont-Grasselli waste was alkaline, with a pH range from l^.i to 1J.J,
during two years of waste disposal at the Acid Site. Mass loadings of the
inputs are equivalent to those of Allied Chemical i.e., insignificant compared
to the total inputs. No adverse effects from Du Pont-Grasselli1s wastes were
ever noted at the site or in the Apex.
D-16
-------
In the same manner as NL Industries' and Allied Chemical's wastes, releases
would have been rapidly diluted, dispersed, and transported by currents to
other Bight regions. Since Du Font's liquid waste was diluted, and
transported out of the Bight, contaminants did not accumulate in the water;
thus Du Pont-Grasselli dumping is important in a Historical sense, but is not
relevant to current mass loadings.
COMPARISON OF CONTAMINANT INPUTS
Table D-4 compares total inputs of selected contaminants into the iNew York
Bight Apex with total inputs of the two permittees presently Uy/yj using the
Acid Site. All acid waste contaminants are less than l/» oi the total
(column 1). Tne materials now being released at the Ac lu Site do not
represent significant sources of contaminants in the receiving waters.
TABLE D-4. MASS LOADING - NEW YORK BIGHT APEX
(Tonnes/Day)
Inputs
Total Inputs
to Apex
Total Inputs
to Acid Site
NL Industries
Allied
Chemical
Total
Percentage of
Apex Total
due to Acid
Wastes
Suspended
Solids
23,580
12.6
0.06
12.7
0.05
Oil and
Grease
783
0.02
0.02
0.04
0.01
Cadmium
2.41
.01
0.005
NM
NM
Chromium
5.3
0.04
0.005
0.04
0.8
Copper
13.2
0.01
0.005
0.01
0.08
Mercury
0.5
0.01
0.005
NM
NM
Lead
12.4
0.01
0.005
NM
NM
Zinc
32.1
0.07
0.00
0.07
0.2
NM not meaningful
D-17
-------
Appendix E
MONITORING
-------
CONTENTS
MONITORING E-l
Short-Tenn Monitoring E-2
Long-Term Monitoring E-5
Figure E-l Monitoring Stations at and Adjacent to the Acid Waste
Disposal Site in New York Bight E-3
Table E-l Physical and Chemical Oceanographic Monitoring Program at and
Adjacent to the Acid Waste Site in the New York Bight E-4
E-i
-------
Appendix E
MONITORING
The Final EPA Ocean Dumping Regulations and Criteria (.4UCFR 220 to
established the following monitoring requirements (.Part 226.^):
(a) The monitoring program, if deemed necessary by the
Regional Administrator or the District Engineer, as
appropriate, may include baseline or trend
assessment surveys by EPA, NOAA, other Federal
agencies, or contractors, special studies by
permittees, and the analysis and interpretation of
data from remote or automatic sampling and/or
sensing devices. The primary purpose of the
monitoring program is to evaluate the impact of
disposal on the marine environment by referencing
the monitoring results to a set of baseline
conditions. When disposal sites are being used on
a continuing basis, such programs may consist of
the following components;
(1) Trend assessment surveys conducted at
intervals frequent enough to assess the extent
and trends of environmental impact. Until
survey data or other information are adequate
to show that changes in frequency or scope are
necessary or desirable, trend assessment and
baseline surveys should generally conform to
the applicable requirements of 228.13. These
surveys shall be the responsibility of the
Federal government.
(2) Special studies conducted by the permittee to
identify immediate and short-term impacts of
disposal operations.
(b) These surveys may be supplemented, where feasible
and useful, by data collected from the use of
automatic sampling buoys, satellites or in situ
platforms, and from experimental programs.
E-l
-------
(c) EPA will require the full participation of other
Federal and State and local agencies in the
development and implementation of disposal site
monitoring programs. The monitoring and research
programs presently supported by permittees may be
incorporated into the overall monitoring program
insofar as feasible.
SHORT-TERM MONITORING
Short-term monitoring surveys are the responsibility of the permittee and
are designed to assess the immediately observable effects of the waste (a
"special stuay" as uefined in tne Ocean Dumping Regulations; .
Special Condition No. 6 ot the ocean disposal permits issued to Allied
Chemical Corporation (Permit No. II-NJ-G04,) and NL industries, Inc. (Permit
No. II-NJ-014) requires these companies to "continue to implement I theirJ EPA
approved monitoring program as a means ot determining the short term
environmental impacts of ocean dumping of ttheirj waste(s)." In May 1977, the
companies submitted a site monitoring proposal prepared by EGc»G, Environmental
Consultants, to fulfill tne site monitoring requirements. Four monitoring
cruises have been completed at the site (EGfcG, 1977, 1976a, 197bb; ERCU,
1978c;. The information from these cruises provides a sufficient data base to
detect longer term changes at the site resulting from acid waste disposal.
Surveys were made during the summer (.strong thermocline) and winter (no
thermocline) seasons. Nine stations were originally estabiisned: two ^now
one) permanent reference stations northeast of the site, five permanent
stations within the site (a center and tour corner stations.) , and two "waste
transport" stations which are established in a waste plume on eacn cruise
(Figure E-l). Two changes were approved in July 1976 (between the thiru and
fourth survey). One reference station was eliminated and vanadium analyses in
tne water column and sediments were eliminated. For 1979 and 19tiO, only the
summer survey is required. Table E-l summarizes the parameters measured for
the monitoring plan.
E-2
-------
NEW
JERSEY
LX
IF SURFACE CURREls
IS TO NORTH
v
\
\
'
\ ACID WASTE D
' DISPOSAL
DISPOSAL SITE STATIONS SITE p
/VASTE TRANSPORT STATIONS ^
X. .,
IEFERENCE (CONTROL) STATIONS
WT-. '~^
I'^^T*
L HEAVY METALS MONITORED / /
(^
* A
r! £/ /
0\^V^./
JT" iWT2 VV>-:'
- ^ / XWT
' v__ / / " 1 _
l— ^ /•-' 2
IWT ;^)-»
i /' WTi
) q
S2 DS D$3
o^
S5 DS4
) n
WATER COLUMN WJ ,-/ /IF SURFACE CURRENT
iAVY METALS MONITORED 2)-y IS TO
/
BENTHIC REGION /
SOUTHWEST
- 40°20'N
- 40°16'N
40"10'W
LIMITS OF BIGHT APEX
NO LONGER REQUIRED
73°40'W
73°36'W
73°30W
Figure E-l. Monitoring Stations at and Adjacent to the
Acid Waste Disposal Site in New York Bight
E-3
-------
TABLE E-l. PHYSICAL AND CHEMICAL OCEANOGRAPHIC
MONITORING PROGRAM AT AND ADJACENT TO THE
ACID WASTE SITE IN THE NEW YORK BIGHT
Water column sampling
• Winter
• Summer
J depths (suDsurface, mid, bottom; [no longer required]
4 depths I, subsurface, above pycnocline, below
pycnocline, bottom;
Parameter
Temperature
Ssi inity
pH
Dissolved oxygen
Alkalinity
Fluoride
Suspended
Particulate i-iatter
Chlorophyll a
Lron-aissolved
-particulate
Nonierric trace
metals - arsenic,
cadmium, chromium
copper, ieaci, mercury.
n i c ke 1 , t i t am ium ,
zinc
Dissolved
Particulate
Unit of Weasure
°C
o /
/oo
.
ml/ liter
meq/ liter
mg/ liter
ug/ liter
mg/m
ug/ liter
ug/liter
ug/ liter
ug/ liter
Stations
All
All
All
All
All
All
Ail
All
All
All
Center of site
ana reference
i\o. of Samples
Profile
Profile
2
2
2.
2
2
2
2
2
2
2
i>entnic Sampling (Surficial Sediment;
Color
Texture
Trace metals -
iron, arsenic
cadmium, chromium
copper, lead,
mercury, nickel,
titanium, zinc
Qualitative
Description
nig/kg dry weight
J-Site
Center,
reference,
waste
transport
/
2
This sampling program is the minimal design sulticient to detect changes
resulting from acid waste disposal. The effects documented at the site are
transitory (Appendix t>) and have not caused long-term, measurable damage to
populations of organisms indigenous to the site or adjacent areas. Chemical
changes in the water column caused by disposal are brief, and ail values
return to ambient levels well within the 4 hour mixing period (.LkCO,
ii-4
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Harmful effects to the plankton have been shown but only last for a
few minutes. Effects on tue bottom nave not Deen documented, altnough waste
contaminants may reach tne sediments during the winter, when the water column
is well mixea.
Ine physical anu cnemical variables presently monitored were cnosen based
upon the composition of the wastes and the possible effects of waste
discharge. Itie water column sampling is adequate to uetect unusual adverse
effects oi disposal, while tne benthic samples can snow it waste constituents
are accumulating in the sediments. Therefore, uo cnanges in tne present
monitoring program are recommended.
LONG-TERM MONITORING
Long-term monitoring surveys are tne responsiui1ity or tne Federal
government and are designed to assess progressive cnanges caused by waste
uispusal which may oe indicated only by subtle changes in selected character-
istics over time. NOAA-inESA is involved in developing an overall program lor
monitoring the conditions in tne iiignt Apex. One goal of tne i>iht>A Project is
to "determine tne requirements for an efticient monitoring program tnat will
detect environmental change (MciSA, l^/rfbj". Tne "ucean Pulse" program oeing
developed by tne NnFS-banay hook Laboratory will also provioe valuable
monitoring data.
Impetus to tnese formal monitoring programs was given oy tne passage ol cue
National Ocean Pollution Research and Development and Monitoring Planning ^cc
of 197o (.PL y5-27j,), wnicn requires NuAA to develop a 5-year plan tor ocean
pollution research and monitoring. Long range studies and trend assessment ol
waste disposal in a complex oceanograpnic area such as tne New York bigut,
with its multiple contaminant sources, is feasible only by tne comoineci
resources of several agencies under the anticipated NUAA five-year plan.
GP0 B63 212
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