&EPA
United States
Environmental Protection
Agency
Office of Water
Criteria and Standards Division
Washington DC 20460
November 1983
EPA 440/5-83-01
.
Environmental
Impact Statement
(EIS)
Draft
Atchafalaya River Bar Channel
Ocean Dredged Material
Disposal Site Designation
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SUMMARY SHEET
ENVIRONMENTAL IMPACT STATEMENT
FOR
ATCHAFALAYA RIVER BAR CHANNEL
OCEAN DREDGED MATERIAL DISPOSAL SITE
(x) Draft
( ) Final
( ) Supplement to Draft
ENVIRONMENTAL PROTECTION AGENCY
OFFICE OF WATER REGULATION AND STANDARDS
CRITERIA AND STANDARDS DIVISION
1. Type of Action
(x) Adminstrative/Regulatory action
( ) Legislation action
2. Brief background description of action and purpose.
The proposed action is the final designation of the Atchafalaya
River Bar Ocean Dredged Material Disposal Site (ODMDS). The ODMDS
is off the mouth of the Atchafalaya River and is adjacent to and
parallel to the Atchafalaya Bar Channel. The purpose of the
action is to provide an environmentally acceptable area for
disposal of dredged material, in compliance with EPA Ocean Dumping
Regulations.
3. Summary of major beneficial and adverse environmenal and other
impacts.
An important beneficial effect of this action is the provision of
an environmentally and economically acceptable location for
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disposal of dredged material. A specific area for the ocean
disposal of dredged material will be available as one alternative
in planning for dredged material disposal. Adverse impacts
include the burial of benthic organisms, formation of a mound, and
development of a plume during disposal operations. The adverse
impacts will be temporary and occur within the site boundaries.
4. Major alternatives considered.
The alternatives considered in this EIS are (1) no action, which
would continue the interim designation of the existing site
without a decision on its status, (2) final designation of the
interim designated site for continuing use, and (3) relocation of
the existing site to an alternative ocean location (e.g.,
nearshore, midshelf, off the continental shelf),
5. Comments have been requested from the following:
Federal Agencies and Offices
Council on Environmental Quality
Department of Commerce
National Oceanic and Atmospheric Administration
National Marine Fisheries
Maritime Administration
Department of Defense
Army Corps of Engineers
Department of Health, Education, and Welfare
Department of the Interior
Fish and Wildlife Service
Bureau of Outdoor Recreation
Bureau of Land Management
Geological Survey
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Department of Transportation
Coast Guard
National Science Foundation
*
States and Municipalities
State of Louisiana
Governor's Office
Department of Wildlife and Fisheries
Terrebonne Parish
Private Organizations
American Littoral Society
Audubon Society
Center for Law and Social Policy
Environmental Defense Fund, Inc.
National Academy of Sciences
National Wildlife Federation
Sierra Club
Water Pollution Control Federation
Academic/Research Institutions
Louisiana State Unversity
6. The Draft statement was officially filed with the Director, Office
of Environmental Review, EPA.
7. Comments on the Draft EIS are due 45 days from the date of EPA's
publication of Notice of Availability in the Federal Register
which is expected to be .
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Comments should be addressed to:
Janis T. Jeffers
Criteria and Standards Division (WH-585)
Office of Water Regulations and Standards
Environmental Protection Agency
401 M Street, SW
Washington, D.C. 20460
Copies of the Draft EIS may be obtained from:
Criteria and Standards Division (WH-5B5)
Office of Water Regulations and Standards
Environmental Protection Agency
401 M Street, SW
Washington, D.C. 20460
The Draft may be reviewed at the following locations:
Office of Federal Activities
Room 2119
Environmental Protection Agency
401 M Street, SW
Washington, D.C. 20024
Environmental Protection Agency
Region VI
1201 Elm Street
Dallas, Texas 75270
Library
U.S. Army Corps of Engineers
New Orleans District
Foot of Prytania Street
New Orleans, Louisiana 70118
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SUMMARY
PURPOSE OF AND NEED FOR ACTION
This Environmental Impact Statement provides information regarding the
final designation for continuing use of the Atchafalaya River Bar Channel
Ocean Dredged Material Disposal Site (ODMDS). The Environmental Protec-
tion Agency (EPA) approved the ODMDS for interim use in 1977 (40 CFR
228), based on historical use of the site. The purpose of the proposed
action is to provide the most feasible and environmentally acceptable
ocean location for the disposal of materials dredged from the Atchafalaya
River Channel System.
A disposal site in the ocean is needed to receive materials dredged
from the Atchafalaya River Channel System. Without dredging, operating
depths would decrease due to the heavy sediment load of the Atchafalaya
River and limit economically important ship traffic utilizing the
Channel.
ALTERNATIVES INCLUDING THE PROPOSED ACTION
Three alternatives were considered during the studies regarding the
proposed action of site designation. These were no-action, final desig-
nation of the interim designated ODMDS, and relocation of the ODMDS.
Non-ocean disposal alternatives were not considered in the EIS. The
designation of an environmentally acceptable ocean disposal site is
independent of individual project requirements. Non-ocean alternatives
for disposal of dredged material must be evaluated for each Federal
project or permit application. Designation of an ocean disposal site
provides an alternative in the range of options for the disposal of
dredged material.
If no action is taken, the interim designation of the ODMDS would
continue since there is no specific termination date. However, approval
of the site was conditional, pending completion of any necessary studies
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and evaluation of its suitability for continued use. The environmental
studies are completed with the results presented in the EIS. Thus, in
accordance with §228.5(c) of the ODR, a decision regarding the continued
use of the site is required and no action is considered an unacceptable
alternative.
The interim designated site was evaluated according to criteria
established in the ODR. The site has been in use for the disposal of
dredged material for over forty years without resulting in adverse
environmental effects outside the site boundaries. Only minimal effects
are apparent within the site boundaries. The site is in the high-energy
inshore area where waves, currents, wind, and tidal actions constantly
mix and redistribute the sediments. Thus, the disposed dredged material
is dispersed gradually over the area. Burial of bottom organisms during
disposal operations will occur within the site, however, the biotic
community of this area is highly adapted to perturbation. Continued use
of the site is not expected to interfere with the biological life of the
area or with other uses of the ocean.
Relocation of the ODMDS to another nearshore area, a mid-shelf area,
or off the Continental Shelf was considered. It was determined that
relocation of the ODMDS to any of these alternative areas would not
result in environmental advantages, but would increase the dredged
material disposal costs. Because of this, relocation of the ODMDS was
not considered to be a viable alternative. Final designation of the
existing interim designated ODMDS was determined to be the preferred
alternative.
AFFECTED ENVIRONMENT
The Atchafalaya River Bar Channel ODMDS is located off the Louisiana
Coast roughly in the middle of the chenier plain physiographic region to
the west and the deltaic plain to the east. The coast is a complex
mixture of wetlands, uplands, and open water influenced by sediment
deposition from the Mississippi and Atchafalaya Rivers. The coast is
marked by many inlets that allow connection with numerous shallow bays
such as the Atchafalaya Channel.
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The climate of the Louisiana coast is a mixture of tropical and
temperate conditions with moderate temperatures and abundant rainfall.
The annual mean air temperature is about 23° C with July and August being
the warmest months and January the coldest month. While precipitation
occurs throughout the year, it is generally intense in summer and early
autumn with the greatest amount of rainfall being associated with
tropical storms. The annual precipitation in New Orleans is about 137
cm. Hurricanes occur in the area on a average of one in four years.
Circulation in the Gulf of Mexico is complex and influenced by the
Loop Current, tides, winds, and river discharge. The major feature of
broad scale circulation in the Gulf is the Loop Current which, as a
continuation of the Yucatan Current, enters the Gulf through the Yucatan
Strait. Local currents in the vicinity of the ODMDS are predominantly
influenced by winds, and to a lesser degree, tides, Loop Current
intrusions, and river flow. Net flow is to the northwest throughout most
of the year. However, rapid flow reversals to the southeast occur
periodically and are well correlated with similar changes in wind
direction. Current speeds generally range from 10 to 40 cm/sec at the
OEMDS. Minimum speeds of 5 to 30 cm/sec occur during June, July, and
August; whereas, the highest recorded current speeds range from 70 to 140
cm/sec and occur during strong winter storms.
Plankton communities at the ODMDS are typical of nearshore Continental
Shelf waters in the Gulf of Mexico. Both marine and fresh water
phytoplankton species exist in the nearshore region off Atchafalaya Bar.
Dominant species are generally marine diatoms, except during summer when
marine dinoflagellates occur in large numbers. Dominant zooplankton
species vary seasonally near the ODMDS. Copepods are the most common
zooplankton collected throughout the year. Other zooplankton that are
periodically present in large numbers include pteropods, ctenophores,
cladocerans, and chaetognaths.
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TWo general types of demersal fish communities occur on the
continental shelf of the northern Gulf of Mexico; the white shrimp
grounds community and the brown shrimp community. The range of the white
shrimp community generally extends from depths of 3m to 22m, whereas the
brown shrimp community generally occurs in depths from 22 to 90m. The
Atlantic croaker and other sciaenids, including sand and silver seatrout
and various species of drum, are the dominant demersal fish in the white
shrimp community. The longspine porgy, inshore lizardfish, blackfin
searobin, and spot are typical species of the brown shrimp community.
Extensive oil and gas development occurs in the Atchafalaya area.
Within three areas off Atchafalaya Bay, i.e., South Marsh Island, Eugene
Island, and Ship Shoal, 26.9% of Louisiana oil and gas fields occur. A
portion of the ODMDS is located within leased blocks, and one platform is
located in the southern corner of the ODMDS. Other activities that occur
in the vicinity of the ODMDS include recreational and commercial fishing,
marine recreation and navigation.
ENVIRONMENTAL CONSEQUENCES
In general, few significant adverse impacts have resulted from
previous dredged material disposal in the Atchafalaya ODMDS. Increases
in turbidity, releases of nutrients or trace metals, and reductions of
benthic faunal abundance and diversity are short-term effects which would
occur within the ODMDS. Results from the Dredged Material Research
Program indicate that impacts within the disposal site are minimized when
dumping occurs in naturally variable, high-energy environments. The
ODMDS is situated in a dynamic, nearshore environment, thus, long-term or
cumulative impacts will be minimal.
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Limited interferences with nearshore fisheries may occur during and in
the immediate vicinity of the dredged material dumping. The ODMDS is
located within passage areas of nekton that seasonally migrate to and
from the estuaries, bays, and Gulf during their life cycle. Any such
interferences would be of short duration and limited because the ODMDS
represents a small percentage of the total nearshore fishing grounds.
Since pipelines are used for disposal of dredged material at the
ODMDS, there may be some temporary blockage of the navigation channel
during dredging operations. Cooperation between the dredgers and vessel
operators can minimize navigational interruptions. This same type of
cooperation can minimize any conflicts with oil and gas exploration and
production as well as with other ocean activities in the area.
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Chapter 2
ALTERNATIVES INCLUDING THE PROPOSED ACTION
The proposed action (chapter 1) is the final designation of the Atchafalaya
Ocean Dredged Material Disposal Site (ODMDS). The Ocean Dumping Regulations and
Criteria (40 CFR 220-229, amended December 1980) approved certain historically
used ocean sites for disposal of dredged materials, including the Atchafalaya
site. Approval was on an interim basis "pending completion of baseline or trend
assessment surveys." The ODR states in part "....§228.5(3) If at anytime during
or after disposal site evaluation studies, it is determined that existing
disposal sites presently approved on an interim basis for ocean dumping do not
meet the citerial for site selection set forth in §§228.5-228.6, the use of such
sites will be terminated as soon as suitable alternative disposal sites can be
designated "
This EIS presents the findings from site evaluation studies of the Atchafalaya
interim designated ODMDS. Utilizing these findings, three alternatives were
considered. These alternatives presented below include: (1) No Action; (2)
Final Designation for Continuing Use of the Interim Designated Sites; and (3)
Relocation of the ODMDS.
Non-Ocean disposal alternatives were not evaluated since the selection and
designation of an environmentally acceptable ocean disposal site is independent
of individual project requirements. This does not mean that land-based disposal
or any other feasible alternatives mentioned in the Environmental Protection
Agency's (EPA) Ocean Dumping Regulations and Criteria (40 CFR §227.15) are being
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permanently set aside in favor of ocean disposal. The need for ocean disposal
must be evaluated for each Federal project or permit application. These
evaluations include considerations of the availability and environmental
acceptability of other feasible alternatives. Designation of an ocean disposal
site presents one option for the disposal of dredged material.
NO ACTION ALTERNATIVE
The interim designation of the Atchafalaya OCMDS does not have a specific
termination date. If no action is taken, the interim designation of the existing
ODMDS would continue for an indefinite period. However, the interim status
provided in the ODR was not intended to remain indefinitely. The site was
approved for dredged material disposal pending completion of any necessary
studies and evaluation of its suitability for continued use. The environmental
studies of the site have been completed and, in accordance with §228.5(c) of the
ODR, a decision on its use is required. Thus, the no action alternative is not
considered to be an acceptable alternative.
ENVIRONMENTAL EVALUATION OF EXISTING SITE
An environmental evaluation was made of the interim designated ODMDS to
determine its suitability for continued use. The eleven specific criteria
(§228.6) and the five general criteria (§228.5) of the EPA Ocean Dumping
Regulations and Criteria (ODR) were used to conduct the evaluation. The
evaluation was based on data obtained in the EPA/IEC site surveys and other
available information. Any station numbers in the text reference the survey
report contained in the Appendix. The results of the evaluation were as follows:
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Specific Criteria (228.6)
(1) Geographical position, depth of water, bottom topography, and distance
fron coast;
The Atchafalaya OCMD6 is located east of and parallel to the
Atchafalaya River Bar Channel. Its corner coordinates are 29020'50"N,
91°24'03"W; 29°11I35"N, 91°31'10"W; 29°lll21"Nf 91031'37"W; and
29°20'36"N, 91°23'27"W. The coordinates as stipulated in the CDR
correctly describe the boundaries of the site historically used for the
disposal of dredged material (see Figure 1-1).
The Continental Shelf is approximately 100 miles wide off the
Atchafalaya Basin. It is a gentle sloping (less than 1°) submarine plain
with many isolated sea knolls and sea mounts (Weissberg et al., 1980a,
1980b; DOI, 1978). The Atchafalaya ODMD3 is located in the nearshore
area of the plain. The site gently slopes at about 0.01° from about 2m
depth at its nearshore end to about 6.6m at its seaward end. Except for
being located adjacent to the dredged channel, the small area occupied by
the ODME6 is typical in depth and bottom topography to a much larger area
off the mouth of the Atchafalaya River.
The center of the Existing OCMD6 is approximately 14 nmi from the
mainland shore. However, in the broadest sense, the site must be
considered to be much closer to the "coast". Nsrth Point of Point au Fer
Island is about 2 nmi east of the northern end of the Existing Site.
Point au Fer is a massive shell reef that lies about 3 nmi shoreward of
the Existing OCMEB; this reef is roughly 0.5 nmi wide and extends nearly
20 nmi across the mouth of Atchafalaya Bay (CE, 1978). The Existing
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OCMDS extends along the Atchafalaya Bar Channel about 12 nmi seaward from
the nearest point within the site to Point au Fer.
(2) Location in relation to breeding, spawning, nursery, feeding, or passage
areas of living resources in adult or juvenile phases;
The northwestern Gulf of Mexico is a breeding, spawning, nursery, and
feeding area for shrimp, menhaden, and bottomfish. Seasonal migration
between the estuaries and the Gulf is a localized passage activity and is
most intensive in the spring and fall.
Two general types of demersal fish communities occur on the continental
shelf of the northern Gulf of Mexico: the white shrimp grounds community
and the brown shrimp grounds community (Chittenden and McEachren, 1976).
The -range of the white shrimp community in the northern Gulf of Mexico
extends from depths of 3m to 22m. Species in the white shrimp community
are highly estuarine dependent. The Atlantic croaker and other
sciaenids, including sand and silver seatrout and various species of
drums, are the dominant demersal fish (ibid.).
The brown shrimp community generally occurs in depths from 22m to 90m,
although the range is somewhat deeper in the central Gulf (Chittenden and
McEachren, 1976). The longspine porgy, inshore lizardfish, blackfin
searobin, and spot are typical species of the brown shrimp community.
There can be considerable intermingling of fish and shellfish species
between the two communities. Brown shrimp and fish from the brown shrimp
community can occur well inside the white shrimp grounds, sometimes in
relatively high abundance.
White and brown shrimp compose the bulk of the shrimp fishery in the
northern Gulf of Mexico. The penaeid shrimp lifecycle is centered around
numerous productive estuaries which are used as nursery areas during the
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larval and juvenile stages. Mult penaeid shrimp spawn in nearshore
waters, producing many microscopic, semibuoyant eggs. White shrimp spawn
from May to September, whereas, the brown shrimp spawning period appears
to extend throughout the year, with peaks in spring and fall (DOE, 1981).
The eggs hatch within several hours into planktonic nauplii, develop
rapidly through a series of larval stages, and are transported landward
toward estuaries. Three to five weeks generally elapse between hatching
and entry of the postlarval shrimp into brackish estuaries (Kutkuhn,
1966). Once in the estuaries, the postlarvae rapidly metamorphose into
juvenile shrimp, growing quickly, and reaching commercial size in two to
four months. The adult shrimp then leave the estuaries and return to the
Gulf (Kutkuhn, 1966). The major offshore movement of white shrimp occurs
in the late summer and autumn (DOE, 1981). Brown shrimp begin their
return to the Gulf in the late May-early June; their migration continues
at least until August when offshore populations peak (DOE, 1981; Barrett
and Gillespie, 1973).
The Existing ODMDS represents a very small area (8.57 nmi2) of the
total range of the white and brown shrimp and their related communities.
During their migration to and from the Atchafalaya River estuarine area,
they may use one of a number of passages through Point au Per Reef.
During periods of active dredging and disposal this one passage route
would be partially restricted. However, the restriction would only be in
the vicinity of the dredging and disposal operation and alternative
migration routes would be available.
Six species of endangered marine mammals (sperm whale, black right
whale, humpback whale, sei whale, fin whale, and blue whale) have been
sighted in the northern Gulf of Mexico (Weissberg et al., 1980a). Most
were chance sightings and do not indicate the presence of indigenous
populations (DOI, 1977). All of the endangered marine mammals are rare
in the northern Gulf of Mexico (ibid.). Several threatened or endangered
species of marine reptiles also occur in the northern Gulf of Mexico
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(Weissberg et al., 1980a). Endangered brown pelicans nest along the
Louisiana shoreline. A colony of brown pelicans presently exists at
Queen Bess Island, 65 nmi east of the Existing Site (Schreiber, 1980;
Blus et al., 1979).
The Existing Site is quite small in comparsion to the overall range of
the known threatened or endangered species. While some may visit the
Existing Site as transients, they should not be affected by disposal of
dredged material at the Existing Site.
(3) Location in relation to beaches and other amenity areas;
There are no known recreational parks or beaches in close proximity to
the Existing ODMDS.' The nearest point of land is North Point of Point au
Per Island; about Z nmi from the north end of the Existing ODMDS. It may
be possible to observe the disposal plume from the Point or from boats
that may be in the vicinity during the active period of dredged material
disposal within the site. The plume is expected to quickly disappear
after completion of the disposal operations. Except for the minor
effects of these limited observations, there should be no effects on the
aesthetics of the area.
Recreational fishing and boating occur throughout the area in the
vicinity of the Existing OCMDS. Ship Shoal is located approximately 25
nmi east of the Existing ODMDS, and Trinity Shoal and Tiger Shoal are
located about 25 nmi west of the site. Smaller fishing shoals are
located within 2.5 nmi of the Existing ODMDS (DOC, 1980a,b); Point au Fer
Reef is located shoreward of the Existing Site (CE, 1978).
There will be some interference with the recreational activities during
disposal operations and in the immediate vicinity. This interference
will be restricted to the relatively small area of the Existing Site
being utilized at the particular time for dredged material disposal. The
area affected will be quite small im comparsion with the total area
available for recreational activities.
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(4) Types and quantities of wastes proposed to be disposed of, and proposed
methods of release including methods of packing the waste, if any;
Over a 10-year period, the average volume of material dredged from the
Atchafalaya every 2-2 1/2 years was 8,625,000 yd3 (Pendergraft,
1982)*. The dredged material generally consisted of approximately 39 to
44% silt and 50 to 56% clay with a small amount 4 to 6% of fine-grained
sand (CE, 1978). The material is removed from the Atchafalaya River
Channel using a cutterhead pipeline dredge and released as a uncohesive
slurry within the Existing Site.
It is expected that the bulk of future dredged material disposals will
follow the past disposal pattern respect to types, quantities, and
methods of release. However, from time to time, minor amounts of dredged
material from other areas in the general vicinity may be considered for
disposal in the site. This material would be transported and released
from barges.
Any material disposed of at the site would be required to comply with
the criteria of the Ocean Dumping Regulations and any other appropriate
requirements. None of the material will be packaged in any way.
(5) Feasibility of Surveillance and Monitoring;
The Existing ODMDS is close to shore which facilitates surveillance of
the site. Operational observations can be made using shore base radar,
aircraft, shipriders, and day use boats.
*Thomas Pendergraft, U.S. Army Corps of Engineers, New Orleans District, Personal
Communication.
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In addition to being close to shore, the Existing ODMDS is shallow.
These features minimize travel time and operations time for most
sampling. Monitoring also will be facilitated by the data base that has
been established for the Site.
(6) Dispersal/ horizontal transport and vertical mixing characteristics of
the area, including prevailing current direction, if any;
Current patterns in the vicinity of the Existing ODMDS are highly
complex. While tides, Loop Current intrusions, and river flow may affect
the local currents, these currents are predominantely influenced by
winds. Thus, the direction and velocity of the currents varies
throughout the year.
\
Winds are a particularly strong driving force in the late autumn,
winter and early spring. Net water flow in the winter is to the
northwest, however, rapid flow reversals to the southeast occur
periodically and are well correlated with similar changes in wind
direction (Weissberg et al., 1980a,b; Grout and Hamiter, 1981).
Nearshore current patterns are somewhat more complex in summer. In the
absence of strong winds and the presence of a stratified water column,
current patterns become considerably less distinct. Net flow in summer
can be either to the east or the west (ibid.). Spin-off eddies from the
Loop Current occasionally enter the region, producing flows to the
southeast near the Existing Site (Weissberg et al., 1980a,b).
Current speeds generally range from 10 to 40 cm/sec in the vicinity of
the Existing Site. Minimum speeds of 5 to 30 cm/sec occur in June, July,
and August, whereas, the highest recorded current speeds in the vicinity
range from 70 to 140 cm/sec and occur during strong winter storms
(Weissberg et al., 1980a,b). Stagnant periods with little or no current
motion have been recorded in April, May and July and may last for as long
as six days (ibid.). One study during dredged material disposal
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operations indicated currents may range from 2 to 25 cm/sec in a
southeast direction (Schubel et al., 1978). Current speeds may reach
200 on/sec during hurricanes which occur about once every four years
(Weissberg et al., 1980a; DOI, 1978).
In the absence of strong currents, the bulk of the dredged material
being disposed settles on the bottom of the particular area of a site
being used at that time. A portion of the plume (fines) will be
transported in the direction of the current over a wider area of the site
and to some extent outside the site. This material will eventually
settle over a wide area.
Currents in the area reach velocities sufficient to resuspend the
disposed dredged material. The resuspended material will be transported
in the direction of the current causing the resuspension. During these
periods, constant mixing of the dredged material and sediments originally
in the area takes place. The mixed dredge material and background
sediments settle as the velocity decreases and are resuspended when some
event again raises the current velocity.
The dredged material represents a small portion of the material carried
into the general area by the runoff of the Atchafalaya River. Initially,
during the dredged material disposal, a mound may be formed within the
Existing Site. However, periodic resuspension of the dredged material
will result in the disappearance of the mound through dispersal and
horizontal transport. The net result will be the remixing of dredged
material with other materials from the original source. Thus, while
there will be dispersal and horizontal transport of the dredged material
from the site, it is not expected any long term detrimental effects on
the environment of the area will occur.
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(7) Existence and effects of current and previous discharges and dumping in
the area (including cumulative effects);
No mounds within the site were detected during EPA/IEC surveys
performed during December 1980 and May-June 1981(Appendix). While there
were spacial and temporal differences in the results for various
parameters, no material differences between sampling stations within the
site and control stations both east and west of the site were detected.
No effects from dredged material disposal could be identified in the
water column, sediments, or benthos of the site. The most recent dredged
material disposal prior to the surveys took place during February 1979.
SEDIMENT CHARACTERISTICS
\
Surficial sediments during both surveys were predominantly silts and
clays at all stations, but exhibited some temporal and spatial textural
variability. Results were similar to previous observations within and
adjacent to the ODMD3 (CE, 1978). Overall ranges for percentages of
sand, silt and clay were 0.1 to 17.1%, 31.7 to 55.1%, and 28.1 to 68.2%,
respectively. Gravel content was minimal at all stations. Clay content
increased somewhat at most stations between the December and May-June
surveys, whereas percentages of sand and silt usually decreased.
Chemical
Concentrations of trace metals in surficial sediments generaly
exhibited little variation over the survey area. Mean (n=40)
concentrations (and ranges) over both surveys were 3.0 ug/g (1.8 to 4.4
ug/g) for arsenic, 0.15 ug/g «0.08 to 0.33 ug/g) for cadmium, 1.9 ug/g
(0.8 to 2.9 ug/g) for chromium, 10 ug/g (7.5 to 16 ug/g) for copper,
0.055 ug/g (0.037 to 0.078 ug/g) for mercury, 590 ug/g (250 to 950 ug/g)
for manganese, 5.5 ug/g (3.9 to 9.1 ug/g) for nickel, 16 ug/g (9.7 to 24
ug/g) for lead, and 25 ug/g (17 to 45 ug/g) for zinc.
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Total organic carbon (TOC) concentrations in sediments, determined only for
the December survey, also showed little variability and were generally low.
Values ranged from 0.15 to 8.2 mg/g, with an overall mean of 1.84 mg/g. No
spatial patterns were apparent.
Concentrations of cyanide and phenols were generally below detectable levels.
Cyanide was detected at low levels (<0.7 ug/g) at a few stations, both inside and
outside the OCMDS, during each survey; no spatial trends were evident. Cyanide
levels were also low «0.5 mg/g) in a previous study of the ODMDS and vicinity
(CE, 1978). Phenols, determined only in December, were not detected in any of
the samples.
Sedimentary CHC concentrations at stations inside and outside the ODMDS were
generally low, and only detectable for dieldrin, pp'DDE, pp'DDD, and PCBs
(Arochlors 1016 and 1254). PCB (1254), DDE, and ODD were present in measurable
quantities during both December and May-June surveys; concentrations ranged from
2.2 to 5.6 ng/g, and were similar between stations and surveys. Dieldrin (2.2 to
4.7 ng/g) was detected only in December, whereas PCB (1016) was present only
during May-June (26 to 74 ng/g).
Oil and grease concentrations vrere high (8 and 15 mg/g) at one station during
December 1980; concentrations at the remaining stations ranged only from 0.4 to
2.2 mg/g over both surveys. The reason for the elevated levels at the one
station is unclear.
Total hydrocarbon concentrations ranged from 98 to 125 ug/g, and did not vary
systematically between stations or surveys. Saturated hydrocarbon levels (55 to
77 ug/g) were somewhat higher during May-June than December, whereas aromatic and
olefinic hydrocarbon concentrations were similar during the two surveys (40 to 65
ug/g). No obvious differences existed between sediments from the ODMDS and
control areas.
As described above, sediment physical and chemical characteristics were
generally similar within and adjacent to the ODMDS. No effects of dredged
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material disposal could be identified; however, a few relatively high
concentrations for sedimentary chemical constituents (zinc, oil and grease) were
.measured within the ODMD3. The survey area is influenced by shallow water
depths, frequent resuspension of bottom sediments by winds and waves, and inputs
of large quantities of fine sediments from riverine sources. Furthermore,
dredged materials released at the ODMES are similar to background sediments in
the vicinity, and are probably widely, distributed by natural processes after
deposition.
Elutriate Tests
Elutriate tests were made on sediments collected during the May-June EPA/IEC
survey. Results were similar from a station inside the OEMD6 (1) and a station
outside the OEMDB (6). Where differences occurred between the two stations,
releases were generally greater from the station sediments outside the DCME6.
For example, manganese releases were indicated in all replicates at both
stations, but were a factor of two greater from sediments outside the ODMES.
Zinc release occurred in one replicate from each station and, again, was
substantially greater for the station outside the'ODMES. For the remaining trace
metals, small or no releases were detected. Arsenic and cadimum were released in
comparatively small quantities in all replicates. Chromium, copper, mercury,
nickel, and lead were retained and/or scavenged from solution by the solid phase.
TISSUE CHEMISTRY '
Concentrations of trace metals and CHCs in organisms collected in trawls in
the vicinity of the ODMES were measured. Trace metal (cadimum, chromium, copper,
mercury, manganese, nickel, lead, and zinc) levels in two species of penaeid
shrimp (Xiphopenaeus kroyeri in December and Trachypenaeus similis in May-June)
were low, and within or below previously reported ranges for these species in the
general area of the ODMES (Tillery, 1980). Of the trace metals examined,
concentrations were highest for zinc (9.4 to 14 ug/g) and copper (5.1 to 8.9
ug/g); a similar situation was indicated by Tillery's (1980) data. Arsenic
concentrations ranged from 5.9 to 8.5 ug/g; no historical data were available for
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comparison. Mercury concentrations (0.007 to 0.015 ug/g) were low. Trace metal
concentrations were generally comparable for organisms collected inside versus
outside the OCME6. Since different species were collected during the two
surveys, temporal comparisons are not warranted.
CHC levels were determined in shrimp (X. kroyeri) during the December survey
and in crabs (Callineetes similis) during May-June. Of the compounds examined,
only dieldrin, pp'DCE, and PCB (Arochlor 1254) were detected. Concentrations in
shrimp were substantially lower than those in crabs although all values were well
below FDA action/tolerance levels for edible marine organisms. CHC levels in
crabs were somewhat greater inside, relative to outside the ODMD3; data are
insufficient to define any cause for this difference. Levels were similar for
shrimp collected inside versus outside the ODMD3. No historical data for CHCs in
these species were available for comparison; however, levels were comparable to
those summarized by Atlas (1981) for other Gulf of Mexico marine organisms.
MICROBIOLOGY
Low counts of total and fecal coliform bacteria were measured in sediments
during both surveys at the Atchafalaya River ODMD3. In December, total coliforms
ranged from 9 MPN/lOOg at one station (9) to 189 MPN/lOOg at another station
(10). Fecal coliforms ranged from nondetectable (stations 3, 8 and 9) to 99
MPN/lOOg at one station (10). During the May-June survey only two stations (5,
10) were sampled for coliforms in sediments; both yielded very low numbers (Table
A-20).
Crabs and shrimp collected in trawls contained low numbers of total coliforms
during both surveys. Fecal coliforms were not detected in any of the tissue
samples.
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(8) Interference with shippingf fishing/ recreational, mineral extraction,
desalination, fish and shellfish culture, areas of special scientific
importance and other legitimate uses of the ocean;
*
The Existing OCMD6 is outside the navigational channel and thus not in
the path of ocean going vessels. Sane smaller boats may pass over the
site; however, since any mounds are expected to be short-lived, there
should be no interference with this passage. Pipeline dredges and
disposal pipelines may interfere with some shipping traffic by blocking
sections of the channel. This interference can be mitigated by close
coordination between the dredging operators and the shipping interests.
Recreational and commercial fishing occurs throughout the year over the
large region. The Existing Site covers a very small area of the region.
There will be some interference with these activities during the dredge
material disposal operations. However, this interference should be of
short duration and only in the vicinity of the disposal operation. Once
this temporary interference subsides, fishing in the area of the site
should return to that typical of the region.
Recreation in the area generally consists of fishing and boating.
Except for a temporary interference during disposal operations, there
should be no interference with these activities. There are no
recreational beaches in the near vicinity of the site.
There is active oil and gas development in the area occupied by the
Existing Site. Platforms are located to the east, south, and west of the
site. Past experience with use of the site for dredged material disposal
has not indicated interference with the oil and gas exploratory or
production operations. The Existing Site is located adjacent to the
channel which minimizes the transport distance to the disposal site.
Other types of mineral extraction do not occur within the site.
No desalination or artificial fish and shellfish culture facilities
occur within the site. Naturally occurring fish and shellfish within the
site, particularly bottom dwelling types, will be affected by the dredged
material disposal. Some of these may be trapped and smothered.
Dispersion and transport of the dredged material outside the site should
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not adversely affect the fish and shellfish. The material dispersed fron
the site will settle in very thin layers and be mixed with the naturally
occurring sediments of the region.
Cyster beds occur on the shell reefs north of the CDMDS. Since
transport of the suspended materials in the water should be to the
southeast, any affects on the oysters will be minimized.
Nothing of special scientific interest is located within the Existing
Site. Periodically, scientific studies are carried cut in the offshore
region and the bays of the area. Use of the site should not interfere
with these studies. It is not expected that use of the site for disposal
of dredged material will interfere with any other legitimate use of the
ocean.
(9) The existing water quality and ecology of the site as determined by
available data or by trend assessment of baseline surveys;
The water quality and ecology of the Existing OCMDS is generally
reflective of that of the nearshore region off the Louisiana Coast
affected by discharges from the Atchafalaya River. The variations in the
water quality depend on the amount and mixing of fresh water runoff
occurring at the time which is highly variable. Data developed during
the EPA/IEC surveys were generally comparable to historic data for the
area (see Appendix).
WATER COLUMN
In the EPA/IEC surveys, salinities varied widely during both the
December 1980 (15.0 to 26.6°/oo) and the May-June 1981 (4.9 to
35.5°/oo) surveys. Mid-depth dissolved oxygen levels during December
ranged from 9.5 to 10.3 mg/1, whereas May-June values ranged from 6.8 to
8.9 mg/1. A wide range of TSS concentrations (10 to 102 mg/1) were
recorded during the December survey when stormy weather was encountered;
during the May-June survey the range was smaller (23 to 60 mg/1).
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With the exception of the maximum of. 250 NIU at one station in December,
turbidity levels were similar for May-June (7 to 55 NIU) and December (14 to 34
NIU) surveys. Values for'pH were slightly higher in December relative to
May-June with all values ranging between 8.1 and 8.5.
In waters off southeastern Louisiana, concentrations of particulate trace
metals within a given volume of water are largely a function of the quantity of
particles present (Beaton, 1978; Schubel et al., 1978; Tillery, 1980). As
expected, maximum concentrations for most particulate metals were measured at
station 1 in December, where the Total Suspended Solids (ISS) level was also
greatest (102 mg/liter). Overall ranges were 0.20 to 0.62 ug/liter for arsenic,
0.02 to 0.07 ug/liter for cadimum, 0.27 to 0.82 ug/liter for chromium, 0.40 to
1.2 ug/liter for copper, 0.004 to 0.016 ug/liter for mercury, 6.6 to 72 ug/liter
for manganese, 0.32 to 0.91 ug/liter for nickel, 0.46 to 1.9 ug/liter for lead,
and 2.0 to 4.9 ug/liter for zinc.
Concentrations of most dissolved metals during the surveys were somewhat
greater in May-June relative to December. Concentrations ranges for dissolved
metals over both surveys were 1.0 to 1.2 ug/liter for arsenic, <0.07 to 0.16
ug/liter for cadimum, <0.11 to 1.0 ug/liter for chromium, 0.94 to 2.5 ug/liter
for copper, <0.033 to 0.073 ug/liter for mercury, 0.16 to 18 ug/liter for
manganese, 0.38 to 2.0 ug/liter for nickel, 0.05 to 3.2 ug/liter for lead, and
1.4 to 3.2 ug/liter for zinc.
Concentrations of most dissolved chlorinated hydrocarbons (CHCs) examined were
below detectable levels at the two stations measured during both surveys.. Only
dieldrin (0.1 to 4.1 ng/liter), the DDT derivative pp'DDE (24 to 53 ng/liter),
and the PCB Arochlor 1254 (0.4 to 0.6 ng/liter) were present in measurable
quantities. Dieldrin and pp'DDE levels were substantially greater during
May-June relative to December; the higher levels may have been derived from
coastal sources.
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None of the water column parameters measured during the surveys indicated that
dredged material disposal has a permanent measurable effect on water quality in
the area of the OCMD6. Waters off southeastern Louisiana are generally turbid
because of shallow depths and riverine influences. Levels of most parameters
appeared to be typical of the study area.
BIOLOGICAL INVESTIGATION
Benthic samples were taken and trawls made during the December 1980, and the
May-June 1981, EPA/IEC surveys. The results indicated the species were
representative of the area with no major differences inside or outside the
Existing ODMD3.
Macrofauna
During benthic investigation in both December and May-June polychaetes
dominated the macrofauna, particularly Mediomastus californiensis, Paraprionospio
pinnata, and Cossura spp. During the December survey the Little surf clam
Mulinia lateralis was very abundant at three stations (7,8, and 9) probably as a
result of seasonal recruitment characteristic of this species (Parker et al.,
1980). By the following survey in late spring (May-June), M_. lateral is was
abundant only at one station (5; and Table A-14). Other common members of this
assemblage were the carnivorous ribbon worms Cerebratulus cf. lacteus (and other
unidentified rhynchocoel) and the snail Nassarius acutus.
The overall abundance of individuals (individual/m2) generally increased
frcm December to May-June due to greater densities of polychaetes. However,
several sharp declines occurred between surveys at two stations due to reductions
in numbers of Mulinia lateralis.
The ODMD3 is a shallow area periodically disturbed by storms. The benthic
assemblage is dominated by species that live for about 1 year and undergo rapid
population expansions (Parker et al., 1980). Results of the surveys indicated
that most macrofaunal species were patchily distributed throughout the study area
and several, such as Mediomastus spp. and Paraprionospio pinnata, are considered
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opportunistic. Because of the ability of the endemic species to cope with
natural disturbances to their sedimentary habitat, any effects on densities of
these organisms which may been caused by dredged material disposal could not be
discerned.
Epifauna
Approximately 600 individuals representing 8 invertebrate and 14 fish species
were collected from otter trawls in the vicinity of the Atchafalaya River ODMDS.
Macrocrustaceans (shrimp and crabs) comprised the bulk of the invertebrate catch;
particularly important were the Seabob shrimp Xiphopenaeus kroyeri in December,
and the Broken-necked shrimp Trachypenaeus similis and the Lesser blue crab
Callinectes similis in May-June. More fish were collected during May-June
relative to December; the Atlantic croaker Micropogon undulatus was most
abundant.
Macroinvertebrates and demersal fish collected during both surveys are
characteristic of the area. Furthermore, relative numbers of dominant organisms
collected, such as large numbers of sciaenids (drums and croakers), were similar
to results of other studies conducted in the area (Landry and Armstrong, 1980;
Weissberg et al., 1980a,b).
(10) Potentiality for the development or recruitment of nuisance species in
the disposal site;
Past disposals of dredged material at the Existing ODMDS have not
resulted in the development or recruitment of nuisance species. It is
not expected that continued dredged material disposals will result in
such development or recruitment.
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(11) Existence at or in close proximity to the site of any significant natural
or cultural features of historical importance;
Various shipwrecks exist in the general area of the Existing ODMDS.
However, no shipwrecks exist within the site. There are no known other
features of historical importance within the site.
GENERAL CRITERIA (228.5)
(a) The dumping of materials 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 cctnmercial or
recreational navigation.
The Existing OCMDS is located adjacent to and along the Atchafalaya
Channel. This location, involving only short transport of the dredged
material, tends to minimize any interference with other activities in the
marine environment. There may be some interference with fishing and
navigation during the dredging and disposal activities. It is not expected
that there will be interference with these or other marine activities
outside these brief periods.
(b) Locations and boundaries of the 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 contaminants or effects before reaching any beach, shoreline,
marine sanctuary, or known geographical fishery or shellfishery.
There will be a turbidity plume during the actual dredged material
disposal operations. This plume should quickly be dispersed to the point
where it is undetectable from the turbidity naturally occurring in the area.
The nearest point of land is North Point of Point au Per; some 2 nmi from
the north end of the disposal site. It is not expected that turbidity
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resulting fron dredged material disposal will be detectable from the natural
turbidity at North Point.
»
There are no marine sanctuaries in the immediate vicinity of the Existing
Site. Shell Keys and Marsh Island Wildlife refuges are approximately 25 nmi
West of the Existing OEMDS. Fishnet Bank, the closest protected area of
Biological Significance, is approximately 90 nmi south of Existing OEMDS.
Commercial fisheries and shellfisheries exist throughout the region. The
Existing ODMD3 is extremely small in ccmparsion with the total fishing and
shellfishing area of the region.
(c) If at anytime during or after disposal site evaluation studies, it is
determined that existing disposal sites presently approved on an interim
basis for ocean dumping do not meet the criteria for site selection set
forth in §§228.5 - 228.6, the use of such sites will be terminated as scon
as suitable alternative disposal sites can be designated.
The studies to date indicate that the Existing ODMDS meets the
requirements of both §228.5 and §228.6. Surveys of the site indicated that
water quality, sediments, and biological life were generally similar inside
and outside the site. tto adverse environmental effects outside the site
boundaries were detected.
(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-range impacts. The size configuration, and location of any
disposal site will be determined as a part of the disposal site evaluation
or designation study.
The configuration of the Existing OCMD6 probably resulted from ease of
disposal from the Atchafalaya channel dredging areas. The proximity led to
the establishment of a long narrow site paralel to the Channel. Regardless
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of the original considerations, the site lends itself to surveillance of
individual dredged material disposal operations and long term monitoring of
the site.
(e) EPA willf wherever feasible, designate ocean dumping sites beyond the edge
of the continental shelf and other such sites that have been historically
used.
The Existing Site has been historically used for disposal of dredged
material.
OTHER FACTORS CONSIDERED
The Existing Site represents an economical location in terms of disposal
costs. Its location adjacent to and parallel with the Atchafalaya Channel lends
itself to the use of pipeline for dredged material disposal. An alternate
location would result in increased costs due to both the increased transport
distances and need to use different types of equipment.
There should be no interference with military training, testing, and research
activities which are restricted to specifically designated areas. The Existing
Site is located well inshore from these areas.
RELOCATION OF EXISTING SITE
The EPA Ocean Dumping Regulations and Criteria (ODR) state in part
"§228.5 (e) EPA will wherever feasible, designate ocean dumping sites beyond
the continental shelf and other such sites that have been historically used." In
addition to an alternate location off the continental shelf as stipulated,
relocation of the ODMDS to alternative shallow-water and mid-shelf sites were
considered to evaluate relative feasibility.
Relocation of the ODMDS would necessitate changes in dredged material
disposal methods. The location of the existing ODMDS in the near vicinity of the
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dredging areas lends itself to the use of pipelines for transporting the dredged
material to the disposal site. Alternative locations of any distance would
require the use barges or hopper dredges.
Shallow-Water Alternative Site
Productive fishing banks are located east of the existing OCMC6. Oil and gas
development is present throughout the nearshore area. The OCME6 is partially
located in the western edge of an oil and gas lease tract which extends to the
east. Oil and gas pipelines are located directly west of the OCMD6 and platforms
are located to the east, south and west. In addition, fishing banks are located
throughout the nearshore area. After considering the foregoing, it was
determined that an alternative shallow-water OCMDS could be located approximately
eight nmi south and two rmi east of the center of the existing ODMES.
The alternative shallow-water site would be deeper overall (6 m+) than the
existing OCME6 (2 to 6.6m). This variance in depth would not be great enough to
materially change the physical stresses on the bottom sediment at the two
locations. The bottom sediment and biological characteristics of two locations
are practically identical. Thus, the environmental effects of dredged material
disposal at the alternate shallow-water site would probably be quite similar to
those at the existing OEME6.
Surveillance and monitoring aspects of an alternative shallow-water site would
also be similar to those at the existing site.
Relocation of the ODMEB to an alternative shallow water site would subject a
new area of the ocean to the effects of dredged material disposal while offering
no environmental advantage over the interim site.
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Mid-Shelf Alternative Site
The Mid-Shelf area off the coast of Louisiana is a biologically productive
area. Oil and gas lease tracts and pipelines are located throughout the mid-
shelf area. Since the entire area is biologically productive the selection of
an alternative mid-shelf site was based principally on avoidance of the oil and
gas lease tracts and pipelines. It was determined that an alternative site with
center coordinates of approximately 28047'00"N, 91021'00"W would accomplish this
avoidance.
Depths in the area of the alternate mid-shelf site range from 3.6m in the
northeastern corner to 21.6m. Use of the site would need to be limited to the
deeper portions of the area. The site would be approximately 52 km from shore
and somewhat closer and due west of Ship Shoal.
The Mid-Shelf area in the vicinity of the proposed alternate site is
characterized by a gentle slope with no prominent bottom features. Sediments
range from silty clay to silty sand (Weissberg, et al., 1980a).
The Mid-Shelf area, being of greater depth, is less dynamic than the
shallow-water area containing the existing OEMD6. The disposed dredged material
would be subjected to a slower rate of erosion and transport. The slower rate of
transport could result in the depositing of thicker layers of mixed site
sediments and dredged material outside the site boundaries than occurs at the
existing site.
The effects on the bottom organisms within a mid-shelf site would be similar
to those at the existing site. Some bottom organisms would be covered by the
dredged material and smothered. Others would be able to work their way through
the sediment layers and recolonize. Some phytoplankton and zooplankton could be
trapped in the decending plume and destroyed. Nekton should be able to avoid the
plume. Considering the large area occupied and range of the bottom organisms,
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phytoplankton, zooplankton, and nekton, the effects of dredged material disposal
in the relatively small area of the mid-shelf site would be minor.
There would be increased costs associated with a mid-shelf alternative site.
A cutterhead pipeline dredge would no longer be feasible due to the distance and
hopper dredges or barges would be required. Dredged material would be
transported by the hopper dredge or barge and released while the vessel passes
slowly through the site.
Although surveillance and monitoring methods would be similar to those
necessary at the interim site, costs would be increased due to the increased
travel and sampling time. The greater distance and depths of water may require
use of larger vessels and special equipment.
Deep Water Alternative
The deep water region is considered to be the area seaward of the 92 m water
depth contour. While this area is beyond the white and brown shrimp grounds, it
contains the royal red shrimp grounds and major fish harvest areas. Fishing
banks are located in the area. A deep water site should be located well beyond
the shelf-break (Pequegnat et al., 1978); a distance from shore of over 100 mi.
It was postulated a deep water site could be located off the Continental Shelf
directly south of the existing site. No specific site within the area was
selected for evaluation.
The disposed dredged material would probably be dispersed over a larger area
than at a mid-shelf site or the existing site due to of breakup of the descending
plume. Once the sediments reached bottom, they would tend to remain in place
with slow erosion and transport. However neither of the foregoing assumptions
can be confirmed without specific information on the upper water and bottom
currents of the specific site.
The effects of dredged materials disposal on bottom organisms, phytoplankton,
zooplankton, and nekton within the site would be similar to that at the existing
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site or the mid-shelf alternative site. Some bottom organisms, phytopiankton,
and zooplankton would .be trapped and perish. Nekton would be affected to the
extent of having to avoid the descending plume.
The safety hazards of dredged material disposal would be materially increased.
The barges containing the dredged material would be operating in open ocean
waters for long periods of time. In addition, they would need to navigate
through dense oil and gas fields with their associated traffic. The possibility
of emergencies developing which would necessitate dumping the dredged material
prior to reaching the disposal site would increase dramatically.
While surveillance and monitoring could be accomplished, these activities
would be difficult and costly. Surveillance could be accomplished through
reports, ship riders, and overflights. Monitoring would require special
equipment because of the open ocean operation and the great water depths.
The annual dredged material disposal costs would be greatly increased due to
the necessity of acquiring a hopper dredge and perhaps barges. In addition,
dredging costs would be increased because of lost time waiting for return of the
barges.
Relocation Summary Findings
o An alternate to the interim ODMDS could be located in the shallow-water
area, the mid-shelf area, or off-the Continental Shelf.
o No material environmental advantage would result from relocation of the
existing site to alternate shallow-water or mid-shelf areas, or
off-the-Continental Shelf.
- The environmental effects on biological life within the site boundaries
would be similar at all sites.
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- Because of the dynamic nature of the area, erosion and transport of the
mixed site sediments and dredged material would occur at a relatively
fast rate at the existing and alternative shallow-water site. The
transport would result in dispersion of the mixed materials over a wide
area in very thin layers; thus, bottom organisms are not likely to be
smothered. The nearshore benthos is adapted to a shifting substrate.
- Erosion and transport of the mixed sediments at a mid-shelf site would be
slower than in the shallow-water area due to its less dynamic nature..
The transported mixed sediments would settle over a smaller area in
thicker layers. While the possibility of smothering of bottom organisms
outside the site would be minimal, some increased smothering might occur
within the site boundaries.
- Erosion and transport of the mixed sediments at a site off the
Continental Shelf, if it occurs, would be quite slow. Bottom organism
outside the site would not suffer smothering because of the slow nature
of the dispersion. However, the benthic organisms are not adapted to a
dynamic environment.
o Surveillance and monitoring could be accomplished at all sites. They would
be more time-consuming and costly at a mid-shelf alternative site. They
would be difficult and very time-consuming and expensive at a site off-the
Continental Shelf.
o The costs of transporting the dredged material to the disposal site would
increase with the distance of the site from the dredging area particularly
as new equipment would be necessary. An increased annual cost could become
prohibitive, particularly in connection with an alternate site
off-the-Continental Shelf.
Based on the above considerations, relocation of the existing interim
designated OCMDS to an alternate ocean area offers no environmental advantage
over designation of the existing site.
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PREFERRED ALTERNATIVE
The foregoing evaluation results in the following observations regarding the
final designation of the interim Atchafalaya OCMD3 for dredged material disposal.
1. No-action would leave the status of the Existing OEMD6 undetermined, thus,
the suitability of the site for disposal of dredged material would remain
in question. The ODR require the final designation or de-designation of
an interim OCMD6 upon completion of evalutive studies.
2. Relocation of the ODMD6 would subject new ocean areas to the effects of
dredged material disposal without resulting in environmental advantages
over the Interim Site. Relocation also would result in increased cost for
dredged material disposal.
3. The interim site is located in an unstable environment characterized by
high variability in physical factors. Correspondingly, the organisms
which occur there are adapted to natural stresses and are able to recover
more rapidly than those organisms adapted to stable conditions.
4. The Existing OCME6 has been historically used for the disposal of dredged
material. Continued use of the site would subject the area within the
site boundaries to the same environmental effects that have existed for a
number of years. Except for the periodic burial of bottom organisms and
the temporary existence of a disposal plume, these effects have been
minimal.
5. No adverse environmental effects due to dredged material disposal outside
the boundaries of the Existing Site were detected during the surveys of
the site; nor were they indicated by the evaluation. It is not expected
that adverse environmental effects outside the site boundaries will result
from continued use of the site.
Based on the studies and analysis, the preferred alternative is the final
designation of the interim designated Atchafalaya CCMC6 (boundary coordinates
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29°20'50"N, 91°24'03"W; 29°11'35"N, 91032'10"W; 29°11I21"N, 91031'31"W;
29° 20' 36 "N, 91° 23' 27 "W) for disposal of dredged materials.
USE OF THE SITE
Future use of the Atchafalaya River Bar Channel OCMDS for disposal of dredged
material must comply with the EPA Ocean Dumping Regulations and Criteria.
The site designation evaluation was based on the disposal of sediments dredged
from the Atchafalaya River Bar Entrance Channel for channel maintenance. Other
dredged material must be evaluated to ensure its compliance with EPA criteria as
set forth in the ODR and its suitability for disposal at the Site.
Dredged material disposal at the Existing Site has averaged 8,625,000
every 2-2 1/2 years without significant adverse impacts. The amount of material
would be representative of an annual disposal rate since it generally results
from the dredging operation during a calendar year rather than a series of
smaller operations over 2-2 1/2 years. The disposal of dredged material at the
Existing Site at a rate not exceeding of 8.6 million yds^ per year is
acceptable. Any increased rates should be evaluated to ensure such rates are
within the capacity of the site. Disposal operations should be timed to avoid
the spring and fall migration of species between the estuaries and Gulf of
Mexico.
The current methods being used by the CE for disposal are acceptable for
continued use. Other generally used methods of disposal may also be acceptable
after review through the permitting process.
Monitoring of the Site
The Ocean Dumping Regulations require that effects of disposal on a disposal
site and surrounding marine environment be evaluated periodically. Information
used in making the disposal impact evaluation may include data from monitoring
surveys. Thus, "if deemed necessary," the CE District Engineer (DE) or EPA
Regional Administrator (RA) may establish a monitoring program to supplement
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historical site data. The monitoring plan is developed by determining
appropriate monitoring parameters, frequency of sampling, and areal extent of the
survey, Factors considered in making this determination include frequency and
volumes of disposal, physical and chemical nature of the dredged material,
dynamics of the site physical processes, and life histories of the species
monitored.
The primary purpose of the monitoring program is to determine whether disposal
at the sites is significantly affecting areas outside the sites, and to detect
any unacceptable long-term adverse effects occurring in or around the sites.
Consequently, the monitoring study should survey the sites as well as surrounding
areas, including control sites and areas which are likely to be affected (as
indicated by environmental factors, such as prevailing sediment transport).
Results of an adequate survey will provide early indication of potential adverse
effects outside the site.
Monitoring for movement of materials into estuaries or onto beaches or
shorelines is minimized because the dredged material is environmentally
acceptable for disposal in the ocean and is similar to sediments of the
surrounding waters. Many physical parameters will be unaffected significantly
by dredged material disposal. Physical parameters that show large variations
after disposal and return quickly to ambient levels do not require monitoring.
Selected parameters which occasionally vary widely (e.g., sediment
characteristics) may be monitored to separate natural environmental fluctuations
from those caused by disposal of dredged material.
Lease oyster grounds are located at the mouth of Atchafalaya Bay and the
increased turbidity during dredging may stress the oysters if the dredged
material is transported shoreward. Monitoring of the effects of dredged material
disposal on the oyster beds is recommended.
The Existing Site is in a productive fishing area. Although there are no data
to suggest that the existing fishery has been affected adversely as a result of
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previous disposal operations, the monitoring program should include methods for
detecting possible effects on the surrounding fisheries.
The monitoring plan should be designed to detect changes from the historic
characteristics of the site and its immediate surrounding area, and possible
long-term effects on the surrounding area.
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Chapter 3
AFFECTED ENVIRONMENT
Environmental characteristics that may be affected by dredged
material disposal off the Louisiana Coast are described in this chapter.
Characteristics potentially affected by ocean disposal are generally
categorized as geological, chemical, or biological. Ancillary informa-
tion, such as physical oceanography and meteorology, is presented
because these natural physical processes influence the fate and effects
of released dredged material. Commercial and recreational resources
that may be affected by dredged material disposal are also discussed
herein.
ENVIRONMENTAL CHARACTERISTICS
Climate
Climatic parameters of interest at an ODMDS are air temperature,
rainfall, wind, storm occurrences, and fog. Air temperature interacts
with surface waters and, particularly during warm periods, influences
the vertical stability of the water column. Rainfall increases coastal
freshwater runoff, thereby decreasing surface salinity and intensifying
vertical stratification of the water column. Coastal runoff also con-
tributes suspended sediments and various chemical pollutants. Winds and
storms can generate wave and currents which resuspend and transport
dredged material. A high incidence of fog during particular seasons
might affect navigational safety and limit disposal operations.
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The Bermuda High, an extensive and persistent high-pressure cell
located over the southwestern part of the Atlantic Ocean dominates
spring and summer weather in the northern Gulf. By autumn, high
pressure systems over the North American continent strengthen and
strongly influence weather patterns, allowing periodic intrusions of
polar air and storm fronts into the area (DOC, 1980b; Weissberg et al.,
1980b). No specific meteorological data are available for the
Atchafalaya Site; however, the proximity of the Site to the Louisiana
coast is such that it has a climate similar to the central Louisiana
shore and Mississippi Delta.
Coastal Louisiana has an annual mean air temperature of 23° C
(Weissberg et al., 1980b). July and August are the warmest months, with
a mean temperature of 29°C; January is the coldest month with a mean
temperature of 17°C (ibid.). Minimum and maximum temperatures ranged
between -1°C and 38°C over a 19 year period.
Precipitation during late autumn, winter, and early spring is
generally associated with northern frontal activity. Precipitation in
summer and early autumn originates from scattered showers,
thunderstorms, and occasional tropical storms. Measurable precipitation
falls 3-4% of the time from November to March and in August and
September. Winter precipitation generally falls as a slow steady
rainfall. Precipitation is intense in summer and early autumn; the
greatest amount of rainfall is associated with tropical storms in
August, September, and October (DOC, 1980b; Weissberg et al., 1980b;
Brower et al., 1972). Mean annual precipitation in New Orleans is 137
cm (Weissberg et al., 1980b). Snowfall is rare along the coast and the
frequency decreases with increased distance offshore (DOI, 1978).
Coastal fog, formed by warm moist Gulf air blowing over the cooler
Louisiana shoreline, or by the seaward drift of land fog, may be
encountered in nearshore regions. Heavy fog (with visibilities less
than 0.5 nmi) is most common from December to April (DOC, 1980b). Fog
3-2
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occurs 3-5 times per month in October and November, 5-6 times per month
in December, January and February, and about 3 times per month in March
(Fernandez-Partagus and Estoque, 1981). Visibility under 2 nmi occurs
about 1% of the time from December to April and less than 0.5% of the
time during the rest of the year (DOC, 1980b); visibility is less than
0.5 nmi between 0.2 and 0.6% of the time from December to April (U.S.
Naval Weather Service Command, 1970).
The Bermuda High produces weak but consistent spring and summer winds
from the east and southeast (Table 3-1). During winter and late autumn,
wind patterns are highly influenced by continental high pressure
systems, which result in mean winds from the north and northeast (Table
3-1; DOC, 1980b; Wells et al., 1981). Strong winds from the north and
northwest may occur for brief periods throughout the year; however, they
are most common during the winter months (Weissberg et al., 1980b).
Winds are more variable near the coast than over the open Gulf because
of the influence of land and sea breezes, which are produced by
differential heating of the shore and sea and superimposed over general
wind patterns in coastal regions (DOC, 1980b).
Winds are strongest from November to March, with average speeds of 13
kn (Table 3-1). Gale force winds along coastal Louisiana typically
result from polar air masses penetrating the Gulf from the North
American continent. Gales occur between 0.6 and 1.3% of the time from
September to March, and less than 0.5% of the time during the remainder
of the year (DOC, 1980b). Highest wind speeds, up to 175 kn, have been
measured during the passage of hurricanes (Weissberg et al., 1980b).
Two major types of storm systems occur in the northern Gulf of
Mexico. Late autumn and winter storms are generally extratropical
cyclones (northers), whereas summer and early autumn storm activity is
dominated by tropical cyclones. Northers typically occur between
November and March and result from polar air masses penetrating from the
North American continent (DOC, 1980b). Minimum wind speed during a
3-3
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norther is generally 20 kn; severe northers have wind speeds ranging
from 25 to 50 kn (ibid.). From 1 to 6 severe northers may occur each
year, typically lasting 1.5 days; however, the more severe storms may
persist from 3 to 4 days (ibid.).
TABLE 3-1
MEAN MONTHLY WIND SPEED AND DIRECTION
FOR THE CENTRAL GULF COAST AREA, 1952-1971
Source: Weissberg et al., 1980b
Wind Speed
Month kn Direction
January 13.3 N
February 13.3 E
March 12.9 SE
April 12.4 SE
May 10.4 SE
June 9 SE
July 8.1 SE
August 8.5 SE
September 11.4 E
October 11.9 ME
November 13.1 N
December 13.4 E
Annual 11.5 SE
A tropical cyclone is a warm-core, low-pressure, closed circulation
system that develops over warm waters of tropical ocean, and has rotary,
counter-counterwise circulation in the Northern Hemisphere. A tropical
storm is a cyclone with wind speed from 34 to 63 kn. The storm is
classified as a hurricane when wind speeds reach 64 kn or higher.
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Tropical storms typically move into the Gulf of Mexico from the
southeast and turn to a northerly direction as they approach the
Louisiana coast (Crutcher and Quayle, 1974). Tropical storms occur most
frequently between June and October, with a peak frequency in the
Louisiana coastal and offshore region in September (Table 3-2). Between 1899
and 1971, 45 tropical cyclones occurred in the region; 18 of the storms were
hurricanes, with an average occurrence of one event per 4 years (Weissberg et
al., 1980b). The most severe storm to impact the Louisiana coastal area in
recent history was Hurricane Camille, which struck in August 1969 with wind
speeds of 175 kn (ibid.).
Physical Oceanography
Physical oceanographic parameters determine the extent of water
column mixing and sediment transport and affect the chemical environment
at an OCMDS. Strong temperature or salinity gradients inhibit mixing of
surface and bottom waters, whereas waves aid mixing. Naves also
resuspend bottom sediments, thereby affecting the turbidity of the water
and contributing to sediment transport. Currents, especially bottom
currents, determine the direction and influence the extent of sediment
transport in and out of an ODMDS. Tidal currents may contribute to the
transport of disposal material, but usually do not add net directional
effects.
TABLE 3-2
AVERAGE MONTHLY NUMBER OF TROPICAL STORMS AND HURRICANES
IN THE 5° SQUARE BOUNDED BY 25°N-30°N and 90°W-95°W.
Modified from Crutcher and Quayle, 1974
Month June July August September October November
Dates 1 - 30 1-31 1-15 1-10 1-15 1-30
16 - 31 11 - 20 16 - 31
21 - 30
Numbers
of storms 0.15
or hurri- 0.14 0.31 0.12
canes 0.19 0.19 0.12 0.17 0.10 0.02
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WATER MASSES
Water masses in the nearshore Louisiana area are influenced by
freshwater discharge fron the Mississippi and Atchafalaya Rivers and,
locally, from coastal estuaries, and by intrusions of Loop Current water
(Comiskey and Farmer, 1981). Influences from riverine and estuarine
discharges are greater in nearshore than in mid-shelf areas.
Conversely, characteristics of water masses in the mid-shelf region are
influenced to a greater extent by open Gulf waters and broad scale
circulation patterns.
River and tidal discharges influence the temperature and salinity,
as well as concentrations of nutrients, trace metals, and suspended
sediments in nearshore waters (Murray, 1976). Maximum combined seasonal
discharge from the Mississippi and Atchafalaya Rivers occurs in J^pril
(52,000 nvVsec) with minimum discharge occurring in September (6,400
m^/sec), (Barrett et al., 1978). Runoff volumes from other
tributaries feeding the north-central Gulf are highest in May.
Low salinity waters derived from coastal rivers may form a distinct
nearshore boundary layer whose width varies with respect to discharge
volumes and turbulent mixing (Murray, 1976). The extent of vertical and
horizontal mixing within the boundary layer will vary seasonally
depending upon current and wind velocities and density differences
between the freshwater plume and ambient nearshore waters.
Vertical stratification may occur in waters (c.f., Turgeon, 1981;
Fotheringham and Weissberg, 1979). Density stratification results from
low salinity waters, discharged from coastal rivers, overlying colder,
saline bottom waters during a period of minimal vertical mixing
(Fotheringham and Weissberg, 1979). Prolonged vertical stratification
during summer can promote oxygen depletion in bottom waters, resulting
in mass mortalities of infaunal and epifaunal organisms throughout large
areas of the western and central Louisiana Shelf (Fortheringham and
Weissberg, 1979; Harper et al., 1981).
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Water masses at the Existing Atchafalaya ODMDS are predominantly
influenced by freshwater discharges from the Atchafalaya and Mississippi
Rivers, and by intrusions of saline offshore water (Weissberg et al.,
1980a; Murray, 1976; Hall and Bouma, 1976; Fotheringham and Weissberg,
1979). The Atchafalaya River is the major tributary of the Mississippi
River, and transports thirty percent of the total Mississippi River
discharge (Weissberg et al., 1980a). This massive influx of freshwater
has a strong effect on coastal waters in the area.
The coastal zone near the Site is vertically stratified in summer and
well^mixed during winter (Weissberg et al., 1980a,b). Salinity
increases with distance from shore and reflects the dilution of brack-
kish riverine water with greater volumes of saline Gulf water.
Consequently/ salinities are generally higher further offshore than at
the Existing Site (Weissberg et al., 1980a). Summer intrusions of high
salinity bottom waters occur in the mid-shelf area (Fotheringham and
Weissberg, 1979); a strong halocline is evident during the summer at a
depth of 7 to 8m. (Weissberg et al., 1980a). Whether these intrusions
are strong or occur frequently in the Existing Site is not clear.
CIRCULATION AND CURRENTS
Circulation in the Gulf of Mexico is complex and influenced by the
Loop Current, tides, winds, and river discharge (DOI, 1978). The major
feature of broad scale circulation in the Gulf is the Loop Current
which, as a continuation of the Yucatan Current, enters the Gulf through
the Yucatan Strait, penetrates up to 29°N in summer, turns clockwise,
and exits through the Florida Straits. During winter the Loop Current
is confined to the southeastern Gulf, and passes through the Straits of
Florida with little intrusion into the central Gulf (Hubertz, 1967;
Leipper, 1970). Eddy-like rings pinched off from the Loop Current,
carrying momentum, high salinity water, and nutrients, are major
contributors to circulation in the central and western Gulf (Sturges and
Horton, 1981).
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Local currents in vicinity of the Atchafalya OCMDS are predominantly
influenced by winds and, to a lesser degree, tides, loop current
intrusions, and river flow. Net flow is to the northwest throughout
most of the year (Wells et al., 1981; Weissberg et al., 1980a,b).
Winds are a particularly strong driving force in the late autumn,
winter, and early spring. Net water flow in the winter is to the
northwest near the Site, however, rapid flow reversals to the southeast
occur periodically and are well correlated with similar changes in wind
direction (Weissberg et al., 1980a,b; Crout and Hamiter, 1981). Tides
may dominate current direction during winter periods of slack winds;
however, tidal influences result in little or no net water or sediment
displacement at the Site. Periods of tidal dominance are periodically
interrupted by wind-induced water movements which may last for several
days (ibid.).
Nearshore current patterns are somewhat more complex in summer. In
the absence of strong winds and the presence of a stratified water
column, current patterns become considerably less distinct. Net flow in
summer can be either to the east or the west (Crout and Hamiter, 1981;
Weissberg et al., 1980a).
Current speeds generally range from 10 to 40 cm/sec (0.2 to 0.8 kn)
at the Existing Site. Minimum speeds of 5 to 30 cm/sec (0.1 to 0.6 kn)
occur during June, July, and August, whereas, the highest recorded
current speeds in the vicinity of the Site range from 70 to 140 cm/sec
(1.4 to 2.8 kn) and occur during strong winter storms (Weissberg et al.,
1980a,b). Current speeds of up to 200 cm/sec (4 kn) may occur during
hurricanes off Atchafalaya Bay, about once every four years. Vertical
shear stress generally causes current speeds to decrease with depth;
this effect is particularly common when wind is the primary driving
force and the water column is stratified. Stagnant periods with little
or no current motion have been recorded in April, May, and July, and may
last for as long as six days (Weissberg et al., 1980a,b).
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WAVES AND TIDES
Waves in Northern Gulf are a combination of wind-generated waves and
swell entering from the open Gulf. Wave direction generally follows the
wind direction and its seasonal patterns; wind and wave directions are
similar during 80% of the year (Wiseman et al., 1975: cited in Wells et
al., 1981). Ninety-three percent of the waves are under 1.5m high, and
41% of these approach from the southeast quadrant (Table 3-3). Tides
are relatively weak in the Gulf of Mexico.
TABLE 3-3
SUMMARY OF ANNUAL WAVE CLIMATE ALONG LOUISIANA COAST
Source: Wells et al., 1981
Wave* Direction
Height Period E SE S SW Total
(m) (sec)
1.0
1.5
2.0
2.5
24 42 20 14 100
GEOLOGY
Geological information relevant to an ODMDS includes bathymetry,
sediment characteristics, and dredged material characteristics.
Bathymetric data provide information on bottom stability, persistence of
sediment mounds, and shoaling. Sediment characteristics strongly
determine the composition of the resident benthic biota. Differences in
sediment size distribution between natural ODMDS sediments and dredged
material may be used as a tracer to determine the area of influence of
the dredged material. Changes in sediment size at the ODMDS which may
be induced by disposal can produce changes in chemical characteristics
and in the composition of the benthic biota.
4.5
6.0
7.0
8.0
13
9
1
1
21
20
1
0
8
9
1
2
5
8
0
1
47
46
3
4
*Percentages cited are relative to the percentage of time during the
year when wind velocities exceed 10 km/hr; this occurs an average of
43.3% of the year.
3-9
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The Louisiana coastline can be divided into two broad segments: the
chenier plain and the deltaic plain; Atchafalaya Bay lies roughly in the
middle of these two physiographic regions (Wells et al., 1981). The
chenier plain, extending west from Marsh Island, Louisiana to East Bay,
Texas has a relatively smooth and regular shoreline fronted by
intermittent mudflats and breached by small inlets that connect with
shallow marshy estuaries (Wells et al., 1981; Gosselink et al., 1979).
The chenier plain system is a unique sedimentary deposit zone consisting
of beach and dune ridges lying on muddy marsh deposits that have been
overlapped by newly developed mudflat marshes (Shepard, 1973; Weissberg
et al., 1980a). The deltaic plain shoreline is highly irregular and
dotted with numerous bays and small lakes (Wells et al., 1981).
Most of Louisiana is located in the vicinity of the Gulf coast geo-
syncline, the axis of which generally corresponds to the trend of the
present coastline (Weissberg et al., 1980a,b). This geosyncline has
been gradually subsiding since the Cretaceous period because of the
large amount of deltaic sedimentation and deposition from the
Mississippi River and its tributaries.
The continental shelf off eastern Louisiana has been completely over-
lapped by the Misissippi Delta during the past 500 years (Fisk et al.,
1954). Wast of the Delta, a trough extends about 20 nmi to the shelf
edge and can be traced down the gentle outer slope over 50 nmi until it
emerges into the broad fan of the Mississippi Cone (Shepard, 1973).
Adjacent to this trough, the shelf off Atchafalaya Bay extends offshore
about 100 nmi and to the shelf-break, which occurs at a depth of 150m
(ibid.). The shelf grades gently (about 0.04°) out to the continental
slope.
Louisiana's coastal zone is predominantly covered by late Quaternary
sediments (Hall and Bouma, 1976). The continental shelf west of the
Mississippi Delta is blanketed by a thick layer of terrestrial sediments
that grade from sand near the shore to silt and clay further offshore
(Uchupi and Emery, 1968).
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Two major types of deposition occur in the Louisiana coastal area
(Coleman, 1966; cited in Hall and Bouma, 1976). One is a result of
sediment input from present and former Mississippi River tributaries;
examples of this type of deposition are the Mississippi Delta and the
present prograding Atchafalaya River Delta. The other depositional
regime is a result of coastal sediment transport processes, which have
produced features such as mud flats and the chenier plain west of Marsh
Island.
Sediment distribution off Atchafalaya Bay can be attributed to
transport and deposition of suspended sediments from the Atchafalaya and
Mississippi Rivers. Resuspension and redistribution of sediments by
currents and winter storms probably exert a large influence on nearshore
sediments through resuspension and winnowing of fine components.
The Atchafalaya River is a distributary of the Mississippi and
presently carries about 30% of the Mississippi River's total water and
sediment load (Wells et al., 1981). Increasing sediment load in the
Atchafalaya River has resulted in a rapid progradation of the
Atchafalaya River Delta (Van Heerden and Roberts, 1980; Roberts et al.,
1980; wells et al., 1981). Eventually the Delta is expected to expand
throughout Atchafalaya Bay forming extensive marshlands (Van Heerden and
Roberts,1980). The remainder of the river's suspended sediment load is
carried out beyond the Point au Fer Shell Reef, and a portion is
deposited in the vicinity of the Existing Site.
Almost 150 million m^/yr of fine sediments are brought to the Gulf
of Mexico by the Atchafalaya River (Wells et al., 1981). A mud plume
extends from the mouth of the Atchafalaya River into the Gulf throughout
the year, and trails to the west about 75% of the time (Wells and Kemp,
1981). On the order of 50 million m^ of sediment are carried to the
west at about 10 cm/sec in the coastal mud stream; a portion of these
sediments are deposited along the rapidly growing eastern flank of the
chenier plain (Wells et al., 1981). The coastal mud stream transports
3-11
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about an order of magnitude more sediments than can be accounted for in
yearly mud flat accretion along the chenier plain; the remainder of the
sediments may be spread across the inner shelf for as much as 50 rani
(Wells and Kemp, 1981). Spring storm activity can enhance this sediment
transport system and result in suspended sediment transport for more
than 125 nmi to the west (Grout and Hamiter, 1981).
The nearshore coastal area off Louisiana is characterized by a
shallow, gently sloping plain punctuated by sand and shell shoals.
Several shoals are located off Atchafalaya Bay: (1) Ship Shoal, located
25 nmi east of the Existing Site, (2) Trinity Shoal, approximately 25
nmi west of the Existing Site, and (3) Tiger Shoal, located inshore of
Trinity Shoal (DOC, 1980a,b). Two unnamed shoals are located
immediately west of the seaward end of the Existing Site (DOC, 1980a).
The nearshore shoals typically rise 2 to 4m from the bottom to a depth
of 2 to 4m below the water surface (DOC, 1980a). Point au Fer reef is a
massive shell reef that lies about 3 nmi shoreward of the Existing Site;
this reef is roughly 0.5 nmi wide and extends nearly 20 nmi across the
mouth of Atchafalaya Bay (CE, 1978).
The Existing Site lies in 2 to 7m of water. The Site is shallowest
near the entrance to Atchafalaya Bay and slopes gently at about 0.01° to
the southwest. Recent navigation charts of the area show no evidence of
mounding (DOC, 1980a). There is a small unidentified obstruction near
the center of the Site (ibid.).
Sediments on the shelf off Atchafalaya Bay range from sand to clayey
silt to silty clay. Nearshore sediments are predominately (>95%) silt
and clays. Sediments become increasingly coarse in the seaward
direction; at approximately the 10m contour sediments are predominately
(>70%) sand (Hausknecht, 1980; Weissburg et al., 1980b). Seaward of the
10m contour, sediments consist of clayey silts and silty clays. Grain-
size generally becomes coarser during the winter months due to the
resuspension of silts and clays by storm turbulence (Hausknecht, 1980).
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Sediments over this region are chiefly of terrigenous origin,
containing less than 30% calcium carbonate (Uchupi and Emery, 1968).
The shelf also contains numerous hills largely composed of salt domes
and partly of mud diapers (Uchupi and Emery, 1968; Shepard, 1973).
During EPA/IEC surveys, surficial sediments in the Existing Site were
predominantly silts and clays. In December 1980 and May-June 1981, the
percentage of fines (silt and clay) and sand ranged from 82 to 100% and
from 0 to 1% respectively. The clay fraction was slightly higher in
May-June than in December. This was probably a function of lower wave
current energy in late spring and summer relative to winter, and inputs
of fines from the river in spring. Sediment types were generally the
same inside and outside the Existing Site, and no effects were evident
that could be related to dredged material disposal.
Water Column
The" chemical parameters pertinent to evaluation of an ODMDS include
suspended solids, nutrients important to phytoplankton growth (e.g.,-
nitrates and phosphates), dissolved and particulate trace elements
(e.g., Cd, Hg. and Pb), and organics (e.g., PCBs, DDT's, and phenols).
High levels of suspended solids can reduce light penetration through the
water column, and inhibit phytoplankton productivity or clog respiratory
structures of fishes and other organisms. Nutrients are essential for
growth and reproduction of phytoplankton, however, under certain
conditions and at elevated levels, these nutrients can promote
eutrophication and subsequent depletion of dissolved oxygen.
Several trace elements are necessary micronutrients for life
processes of organisms; however, metals such as mercury and cadmium can
be toxic when present in relatively high levels in water or in food
sources. Many chlorinated and petroleum hydrocarbons are also toxic and
can be bioaccumulated if ingested in sufficient quantity by marine
organisms.
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TEMPERATURE
Average winter surface water temperature in the Gulf of Mexico grade
from 18°C in the northern Gulf to 24°C in the southern Gulf, with strong
onshore-offshore temperature gradients over the shelf area. Curing
the summer surface temperatures are nearly uniform across the Gulf and
average 29°C (DOI, 1978).
Temperatures in shallow coastal water areas closely follow seasonal
changes in air temperature (Hall and Bouma, 1976; DOI, 1978). Typical
summer temperatures range from 27 to 30°C; winter temperatures are
between 12 to 22° (Vfeissberg et al., 1980a, 1980b). Vertical
temperature stratification may periodically occur in shelf waters during
summer following intrusions of cooler, more saline Gulf waters
(Weissberg et al., 1980a).
SALINITY
Salinity distribution in the Gulf of Mexico is influenced by the Loop
Current, precipitation, river discharge, evaporation, circulation, and
mixing (DOI, 1978). Open Gulf salinities are generally around 35°/oo
(Arthur D. Little, Inc., 1973). Discharge from the Mississippi and
Atchafalaya Rivers, however, create a nearshore band of lower salinity
water (DOI, 1978).
Salinity varies considerably in the nearshore area. Surface
salinities in the Mid-Shelf area range from 20.4°/oo in early April to
29.9°/oo in November; bottom salinities range from 22°/oo in early
3-14
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April to 30.9°/oo in March (Vfeissberg et al., 1980a). Salinity
stratification, resulting from a brackish layer of mixed river and Gulf
water overlying highly saline Gulf Water, is common in the Louisiana
nearshore zone during spring and summer (Weissberg et al., 1980a,b). In
winter, wind and wave induced turbulence mixes the shallow coastal
waters, disrupting summer haloclines.
Salinities varied widely during the EPA/IEC surveys of the Atcha-
falaya ODMDS and its immediate vicinity. Mid-water salinity values
ranged from 15.0 to 26.6°/oo in December 1980 and 4.9 to 35.5°/oo in
May-June 1981. The low salinity (4.9°/oo) in May-June 1981 was
measured at a nearshore station west of the Existing Site. A value of
15.0°/oo was measured at this station in December 1980. Salinities at
all other stations tended toward the higher end of the range in both the
winter and summer surveys.
DISSOLVED OXYGEN
Dissolved oxygen (DO) concentrations in Louisiana shelf waters may
vary with season and depth (Reitsema, 1980; Landry and Armstrong, 1980).
For example, during summer freshwater discharge and/or intrusions of
open Gulf waters may cause density stratification of the water column.
Restricted vertical mixing and oxidation of organic matter in surficial
sediments promotes oxygen depletion in bottom waters. Anoxic or hypoxic
conditions in shelf bottom waters may be an annual phenomenon off
Louisiana (Parker et al., 1980; Reitsema, 1980; Harper et al., 1981).
During winter shelf waters are typically well-mixed vertically due to
increased storm turbulence and reduced river runoff, resulting in
relatively higher oxygen concentrations.
3-15
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EPA/IEC surveys conducted within and around the Atchafalaya OCMDS
found the water at mid-depth to be well oxygenated. DO concentrations
were somewhat higher in winter than spring, with values ranging from 9.5
to 10.3 mg/1 and 6.8 to 8.9 mg/1, respectively.
Shallow waters in the Vermilion Bay - Atchafalaya Bay complex are
typically well-oxygenated; DO concentrations over a two year period
averaged 8.2 mg/1 with no depth related trends noted (Juneau, 1975).
Offshore from Atchafalaya Bay, at approximately the 10m contour, DO
levels range from 7.5 mg/1 at the surface to 0.1 mg/1 in bottom waters
during summer stratification (Parker et al., 1980; Fotheringham and
Weissberg, 1979). In winter, the water column is well- mixed and DO
levels may range from 10 mg/1 at the surface to 8 mg/1 in bottom waters
(Parker et al., 1980; Weissberg et al., 1980b).
pH
Coastal waters may experience some fluctuations in pH values
resulting from photosynthetic activity and river runoff. Thus, there
can be seasonal and non-seasonal fluctuations.
During EPA/IEC surveys the pH within and around the Existing Site
was slightly higher in winter relative to spring. However, all values
(8.1 to 8.5) fell within the normal range for seawater. The lower pH
values may have reflected runoff from the coastal marshes where acid
formation is known to occur. pH values measured in waters further
offshore in the mid-shelf area range from 6.7 to 9.3 with an average
value of 8.1. (DOT, 1976).
NUTRIENTS
Nutrient concentrations in open Gulf and shelf waters off Louisiana
are typically low, except in localized nearshore areas in the vicinity
of coastal rivers and embayments (Brooks, 1980; Barnard and Froelich,
1981; Ho and Barrett, 1977). Factors influencing nutrient concentra-
3-16
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tions in shelf waters include river discharge, coastal currents and
winds, biological activity, rainfall, and proximity to coastal marshes
(Ho and Barrett, 1977; Brooks, 1980). Typical nutrient concentrations
for northern Gulf coastal waters are listed in Table 3-4.
TABLE 3-4
NUTRIENTS RANGES (ug-at/liter) FOR THE NORTHERN GULF COASTAL WATERS
Mean Minimum Maximum Surface Mean
P04 0.10 - 0.40 0.01 - 0.17 0.21 - 4.74 0.03 - 0.32
N03 0.5 - 2.7 0.1 - 0.2 3.5 - 13.8 0.1 - 0.8
Si02 1.7 - 4.6 0.1 - 2.3 4.7 - 13.9 1.2 - 5.6
(dissolved)
Source: Brooks, 1980
TURBIDITY AND SUSPENDED SOLIDS
Turbidity in coastal Louisiana waters is influenced by resuspension
of surficial sediments and runoff from the Atchafalaya and Mississippi
Rivers; discharge plumes from the Atchafalaya River have been detected
as far as 18 miles offshore. Secchi disk measurements have ranged from
0.5 to 6.5m in the Atchafalaya area (Weissberg et al., 1980a, 1980b).
Total suspended solid (TSS) levels vary within Louisiana coastal
waters, but are generally many times higher than levels off the east and
west coasts of the United States (Wells et al., 1981). Wave climate,
bottom texture, and proximity to the Mississippi and Atchafalaya Rivers
and local bayous are factors influencing TSS levels (Wells et al., 1981;
Hausknecht, 1980; Harris, 1972). TSS levels decrease with distance from
shore. For example, nearshore, surface waters within the Atchafalaya
River plume may have TSS concentrations ranging from 200 to 500 mg/1;
whereas offshore waters may contain 30 mg/1 (Wells et al., 1981) and
open Gulf surface waters have TSS levels as low as 0.6 mg/1 (Harris,
1972).
EPA/IEC surveys measured high turbidity within and around the
Atchafalaya ODMDS; values ranged from 7 to 55 nephelometric turbidity
units (NTU) in late spring and from 14 to 34 NTU in winter. A wide TSS
range (10 to 102 mg/1) was measured during December at the Existing Site
3-17
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when storm/ weather was encountered. A smaller TSS range (23 to 60 mg/1), with a
generally decreasing offshore trend, occurred during the May-June survey.
TRACE METALS
Distributions and concentrations of trace metals in the Gulf of Mexico are
variable and related to land runoff, biological activity, anthropogenic inputs,
and physical processes mixing Gulf waters (Frey et al., 1981; Trefry, 1981). The
major source of dissolved and particulate trace metals to the Gulf is discharge
from the Mississippi and Atchafalaya Rivers and, to a lesser extent, from coastal
embayments. In general, dissolved and particulate trace metal concentrations
decrease with increased distance from the input source (Bahr and Hebrard, 1976).
A significant portion of the trace metal concentration is in the particulate
fraction (Trefry, 1981).
Maximum concentrations for most particulate metals at the Atchafalaya ODMDS
were measured during EPA/IEC surveys at Station 1 (center of site) for December,
where the TSS level was also greatest (102 mg/liter). Particulate trace metal
values were slightly lower at control Station 6 (east of site) during May-June
(TSS = 58.7 mg/liter), followed by roughly equivalent concentrations for Station
1 in May-June and Station 6 in December (TSS = 23.0 and 18.5 mg/liter,
repectively). Overall ranges were 0.20 to 0.62 ug/liter for arsenic, 0.02 to
0.07 ug/liter for cadimum, 0.27 to 0.82 ug/liter for chromium, 0.04 to 1.2
ug/liter for copper, 0.004 to 0.016 ug/liter for mercury, 6.6 to 72 ug/liter for
manganese, 0.32 to 0.91 ug/liter for nickel, 0.46 to 1.9 ug/liter for lead, and
2.0 to 4.9 ug/liter for zinc. All concentrations were comparable to ambient
levels reported for nearshore waters in the area (Heaton, 1978; Schubel et al.,
1978; Tillery, 1980).
Concentrations of most dissolved metals during the surveys were somewhat
greater in May-June relative to December. Dissolved metal concentrations appeared
to be inversely related to TSS and particulate metal levels; this inverse
relationship may be caused by scavenging of metals from solution onto sediment
particles (Heaton, 1978). Concentration ranges for dissolved metals over both
surveys were 1.0 to 1.2 ug/liter for arsenic, <0.07 to 0.16 ug/liter for cadmium,
<0.11 to 1.0 ug/liter for chromium, 0.94 to 2.5 ug/liter for copper, <0.033 to
0.073 ug/liter for mercury, 0.16 to 18 ug/liter for manganese, 0.38 to 2.0
ug/liter for nickel, 0.05 to 3.2 ug/liter for lead, and 1.4 to 3.2 ug/liter for
zinc. Although concentrations of certain metals (e.g., manganese and lead)
3-18
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varied widely, all data were comparable to results of previous studies off
southeastern Louisiana (CE, 1978; Beaton, 1978; Fortheringham and Vfeissberg,
1979; Weissberg et al., 1980a,b). No consistent differences in dissolved
metals levels between ODMDS Station 1 and control Station 6 were observed.
ORGANICS
Chlorinated hydrocarbons (CHC) levels are typically low in Gulf of Mexico
waters (Table 3-5). Two main sources of CHC are riverine and atmospheric
inputs (Atlas, 1981).
TABLE 3-5
CONCENTRATIONS OF DDT AND PCS (ng/liter) IN WATERS FROM THE
GULF OF MEXICO
No. Of DDT PCB
Samples Samples Mean Range Mean Range
Mississippi
Delta
Gulf Coast
Open Gulf
14
10
7
1.70
0.35
0.25
0.01-2.9
0.01-0.6
<0. 1-0.6
2.45
1.60
1.40
1.7-3.3
0.1-3.1
<0.1-2.8
(From Giam et al., 1978a. Cited in Atlas, 1981)
Concentrations of most dissolved CHCs examined at the Atchafalaya ODMDS were
below detectable levels during both surveys. Only dieldrin (0.1 to 4.1
ng/liter), the DDT derivative pp'DDE (24 to 53 ng/liter), and the PCB Arochlor
1254 (0.4 to 0.6 ng/liter) were present in measurable quantities. Dieldrin and
pp'DDE levels were substantially greater during May-June relative to December;
the higher levels may have been derived from coastal sources. The maximum
dieldrin concentration measured during the May-June survey (4.1 ng/liter) was
somewhat greater than reported previously (CE, 1978) for the area of the ODMDS
(0.5 to 3 ng/liter); Concentrations of DDTs determined previously in
Mississippi River water and in nearshore waters off Louisiana (CE, 1978; Giam
et al., 1978), were somewhat lower than those reported here. PCB concentra-
tions (detected during the December survey only) were within or below ranges
for the region reported in the literature (CE, 1978; Giam et al., 1978).
3-19
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Sediment Chemistry
A variety of trace contaminants, such as trace metals, petroleum and
chlorinated hydrocarbons, and organic material (ccnmonly expressed as
total organic carbon [TOC]), can accumulate in sediments. Elevated
levels of marine sediment contaminants generally result from
anthropogenic inputs such as municipal and industrial waste, urban and
agricultural runoff, atmospheric fallout from urban centers, and
accidental spillage. Silty and clayey sediments have a greater
absorptive capacity for trace contaminants, and typically have higher
TOC levels than coarser material because of their large surface area to
volume ratio and charge density.
Accumulation of trace elements and chlorinated and petroleum
hydrocarbons in sediments can have negative short term or long term
effects on marine organisms. Many benthic organisms are deposit feeders
which ingest substantial quantities of bottom sediments. The potential
for bioaccemulation of persistent trace contaminants such as mercury,
lead, and chlorinated hydrocarbons by these organisms is of particular
environmental concern.
High concentrations of organic materials can produce anoxic
conditions in sediments resulting in the production of sulfides.
Oxidation of these sulfides is responsible for much of the initial
consumption of oxygen immediately following dredged material disposal.
Significantly lowered oxygen levels in sediments or near bottom waters
can adversely affect marine organisms.
SEDIMENT HYDROCARBONS
The major sources of hydrocarbons to sediments in the. northern Gulf
are discharges from the Mississippi River and other coastal runoff, and
atmospheric and anthropogenic inputs (Atlas, 1981). Concentrations of
sediment hydrocarbons are highest near the Mississippi Delta and other
source areas, and typically decrease with increased distance from shore
(ibid.).
3-20
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TOC concentrations ranged from 0.15 to 8.2 mg/g within and around the
Atchafalaya OCMDS during the EPA/IEC winter survey, and were not
significantly correlated with any other sediment parameters. Spring TOC
concentrations were not measured.
CMC levels in sediments within and around the Existing Site are low
or non-detectable (CE, 1979). During EPA/IEC surveys, only dieldrin
(4.77 ng/g), pp'DDE (2.15 to 4.51 ng/g), pp'DDD (2.23 to 4.05 ng/g), and
the PCBs Arochlor 1016 (ND to 74.1 ng/g) and Arochlor 1254 (5.19 to 22.9
ng/g) were present in measureable quantities.
Concentrations of cyanide and phenols were generally below detectable
levels during the EPA/IEC surveys. Cyanide was detected at low levels
«0.7 ug/g) at a few stations, both inside and outside the ODMDS, during
each survey; no spatial trends were evident. Cyanide levels were also
low «0.5 mg/g) in a previous study of the ODMDS and vicinity (CE,
1978). Phenols, determined only in December, were not detected in any
of the samples.
Oil and grease concentrations were high (8 and 15 mg/g) in both
Station 1 ODMDS (center of site) replicates during December 1980,
EPA/IEC survey; concentrations at the remaining stations ranged from 0.4
to 2.2 mg/g over both surveys. The reason for the elevated levels at
Station 1 is unclear. Since this station is located within the ODMDS,
dredged material disposal must be considered a possible cause. The most
recent disposal to occur prior to the surveys, however, took place
during February 1979. Considering the transient nature of surficial
sediments in this area (Hausknecht, 1980), it is unlikely that any
contaminated dredged material deposits would remain intact for nearly 2
years. Tnis assumption is supported by the reduced oil and grease
concentrations «0.5 mg/g) present at Station 1 during the May-June 1981
survey. Additionally, CE (1978) found oil and grease concentrations to
be low (<0.1 mg/g) in adjacent dredging areas.
3-21
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TRACE METALS
Discharge from the Mississippi and Atchafalaya Rivers is the primary
source of trace metals to sediments in the western Gulf of Mexico
(Tillery, 1980). The major portion of the metal flux into Gulf waters
is associated with the suspended sediment fraction (Presley et al.,
1980). Highest concentrations of most sediment metals are associated
with terrigenous silts and clays on the outer shelf and slope off
Central Louisiana (Holmes, 1973). Within the surficial sediments on the
Louisiana Shelf, trace metal concentrations are variable; however,
levels are often higher in the fine seiments at nearshore areas, and
lower in coarser (sandy) sediments from areas further offshore (DOE,
1978; Comiskey and Farmer, 1981; Tillery, 1980).
Concentrations of trace metals in surficial sediments at the
Atchafalaya ODMDS generally exhibited little variations over the survey
area (EPA/IEC surveys). Mean (n = 40) concentrations (and ranges) over
both surveys were 3.0 ug/g (1.8 to 4.4 ug/g) for arsenic, 0.15 ug/g
«0.08 to 0.33 ug/g) for cadmium, 1.9 ug/g (0.8 to 2.9 ug/g) for
chromium, 10 ug/g (7.5 to 16 ug/g) for copper, 0.055 ug/g (0.037 to
0.078 ug/g) for mercury, 590 ug/g (250 to 950 ug/g) for manganese, 5.5
ug/g (3.9 to 9.1 ug/g) for nickel, 16 ug/g (9.7 to 24 ug/g) for lead,
and 25 ug/g (17 to 45 ug/g) for zinc.
Biology
Described in this section, water column biota include phytoplankton,
zooplankton, and nekton. Benthic biota is composed of infaunal and
epifaunal organisms that are generally sedentary and cannot readily
migrate from an area. The infauna can therefore be important indicators
of environmental conditions. Dredged material disposal will have only
short-term effects on plankton communities because of the transient
nature of the watemasses they inhabit. Nekton generally are not
adversely affected by dredged material disposal because of their high
mobility.
3-22
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PHYTOPLANKTON
The phytoplankton conmunity in Louisiana coastal waters is diverse
and productive containing both marine and freshwater species (Table 3-6)
marine diatoms generally dominate, except during the summer when marine
dinoflagellates occur in large numbers. The abundance of freshwater
species increases in autumn through mid-winter when river discharge
volumes increase. Phytoplankton biomass undergoes large spatial and
temporal fluctuations. Cell density is highest in coastal bays and the
neritic zone, and decreases seaward (Vfeissberg et al., 1980b). Both the
mid-shelf area and nearshore areas have similar patterns of
phytoplankton composition and biomass (Loop Inc., 1975; Weissberg et
al., 1980b).
TABLE 3-6
SEASONAL CHANGES IN DOMINANT PHYTOPLANKTON
SPECIES IN LOUISIANA COASTAL WATERS
GENUS
Dinoflagellates
Ceratium
Exuviella
Goniaulax
Gymnodinium
Diatoms
Asterionella
Biddulphia
Cose inod iscus
Cyclotella
Fragillaria
Guinardia
Lithodesmium
Navicula
Nitszchia
Porosira
Rhizoselenia
Skeletonema
Thalassiosira
Source: Loop Inc., 1975
SEASON
Late Spring
and Summer
X
X
X
X
X
X
X
X
X
X
X
X
Winter Autumn
X
X
X
X
X
X
X
X
X
3-23
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ZOOFLANKTON
Zooplankton in the northern Gulf can be characterized as inhabitants
of any of five zoogeographic zones: oceanic, continental slope
transition, central continental shelf, coastal neritic, and estuarine
zone. These zones are geographically variable, and their boundaries may
reflect influences from water masses and current patterns. Zooplankton
communities in each of the five zones are dominated by copepods;
however, the dominant species may vary between zones. For example,
within coastal areas temperate copepod species (e.g., Acartia tonsa,
Paracalanus crassirostis, Eucalanus pileatus) are typically dominant,
whereas tropical-subtropical species (e.g., Euchaeta marina, Copilia
mirabilis) are dominant in oceanic regions (Comiskey and Farmer, 1981).
Zooplankton densities generally decrease with increased distance from
shore (DOE, 1978; Comiskey and Farmer, 1981).
Dominant Zooplankton species vary seasonally in the waters near the
ODMDS (Table 3-7). Copepods are most commonly collected (Vfeissberg et
al., 1980a, 1980b; Reitsema, 1980). Other zooplanton that are
periodically present in large numbers include pterpods ctenophores, clad-
ocerans, and chaetognaths (ibid.).
TABLE 3-7
DOMINANT ZOOPLANKTON ORGANISMS, BY SEASON
AT WEEKS ISLAND SITE A
Spring
Summer
Dominant
Species
(% of total)
Acartia sp. Cladocera
(>60%)3
Fall
Tempora sp.
Winter
Acartia sp.
Sagitta sp. Tempora sp. Sagitta sp.
(6%)^
Labidocera sp.
(27%)!
Sagitta sp.
1: Copepod
2: Chaetognath
3: Cladoceran (Glass Crustacea)
Source: Reitsema, 1980
3-24
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FINFISH AND SHELLFISH
TWo general types of fish conmunities occur on the continental shelf of
the northern Gulf of Mexico: the white shrimp grounds community and the
brown shrimp grounds community (Chittenden and McEachren, 1976). The
range of the white shrimp community in the northern Gulf of Mexico extends
from depths of 3m to 22m. The community is more developed in the central
Gulf off the coast of Louisiana where some species typical of this
community are found at depths of 100m (ibid.). Species in the white
shrimp community are highly estuarine dependent. The Atlantic croaker and
other sciaenids, including sand and silver seatrout and various species of
drums, are the dominant fish (ibid.) (Table 3-8).
The brown shrimp community generally occurs in depths from 22m to 90mf
although the range is somewhat deeper in the central Gulf (Chittenden and
McEachren, 1976). The longspine porgy, inshore lizardfish, blackfin
searobin, and spot are typical species of the brown shrimp community.
These common species may also occur in the deeper parts of the white
shrimp'grounds, (Table 3-9).
There can be considerable intermingling of fish and shellfish species
between the two communities. Brown shrimp and fish from the brown shrimp
community can occur well inside the white shrimp grounds, sometimes in
relatively high abundance.
Seasonally dominant demersal fish near the Existing Site include sea
catfish, banded and star drum, bighead searobin, and fringed flounder.
The Atlantic cutlassfish, sand seatrout, and banded drum dominated
demersal fish catches in the December EPA/IEC survey. During the May-June
survey, the Atlantic croaker was the most abundant demersal species
(Appendix). Major food items of common demersal fish in the area include
polychaetes, gastropod and bivalave mollusks, shrimps, decapods, and
copepods (Landry and Armstrong, 1980).
3-25
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TABLE 3-8
SCIENTIFIC NAMES OF FISH TYPICALLY FOUND OFF THE LOUISIANA COAST
Common Name
Scientific Name
Atlantic bumper
Atlantic croaker
Atlantic cutlass fish
Atlantic spadefish
Atlantic threadfin
Banded drum
Bay anchovy
Bighead searobin
Blackfin searobin
Blue fish
Blue runner
Cobia
Crevalle jack
Fringed flounder
Great barracuda
Greater amberjack
Gulf butterfish
Gulf menhaden
Inshore lizardfish
King mackerel
Ladyfish
Longspine porgy
Mexican flounder
Pompano
Rock seabass
Sand seatrout
Scaled sardine
Sea catfish
Sheepshead
Silver seatrout
Southern king fish
Spanish mackerel
Spot
Star drum
Striped anchovy
Chloroscombrus chrysurus
Micropogon undulatus
Trichiurus lepturus
Chaetodipterus faber
Polydactylus octonemus
Larimus fasciatus
Anchoa mitchilli
Prionotus tribulus
Prionotus rubio
Pomatomus saltatrix
Caranx fusus
Rachycentron canadum
Caranx hippos
Etropus crossotus
Sphyraena barracuda
Seriola dumerili
Peprilus burti
Brevoortia patronus
Synodus foetens
Scomberomorus cavalla
Slops saurus
Stenotcmus caprinus
Cyclopsetta chittendeni
Trachinotus carolinus
Centropristic philadelphica
Cynoscion arenarius
Harengula pensacolae
Arius felis
Archosargus probatocephalus
Cynoscion nothus
Menticirrhus americanus
Scomberomorus maculatus
Leiostomus zanthurus
Stellifer lanceolatus
Anchoa hepsetus
3-26
-------
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The bay and striped anchovy, Gulf butterfish, and scaled sardine are
typical non-demersal fish harvested in and near the Existing Site
(Appendix; Weissberg et al., 1980b). Other fish that are abundant in the
region of the site, but generally not caught in slow trawls, include lady-
fish, bluefish, Spanish mackerel, rock seabass, Gulf menhaden, Atlantic
bumper, and Atlantic threadfin (Weissberg et al., 1980a, b). Oil rigs in
the Gulf provide reef-like environments for cobia, crevalle jack, greater
amberjack, sheepshead, great barracuda, king mackerel, blue runner, and
Atlantic spadefish (Vfeissberg et al., 1980a).
More than 42 species of shellfish inhabit coastal waters of Louisiana.
Abundant species include seabob shrimp, white shrimp, brown shrimp,
broken-necked shrimp, and blue crab (Table 3-10).
Shrimp are typically the most abundant crustaceans near the Existing
Site throughout the year, although brief squid are also common (Weissberg /
et al., 1980b). Shrimp, crab, and squid made up the bulk of macroinverte-
brates collected at the Existing Site during EPA/IEC surveys. Seabob
shrimp and brief squid were dominant in December, whereas broken-necked
shrimp and the lesser blue crab were the major macroinvertebrates caught
in May-June.
Table 3-10
COMMON AND SCIENTIFIC NAMES OF
SHELLFISH TYPICALLY FOUND OFF LOUISIANA COAST
Source: Landry and Armstrong, 1980
Common Name Scientific Name
Blue Crab Callinectes sapidus
Lesser blue crab Callinectes similis
Broken-necked shrimp Trachypenaeus similis
Broken-necked shrimp Trachypenaeus constrictus
Brown shrimp Penaeus aztecus
Swimming crab Portunus spp.
Seabob shrimp Xiphopenaeus kroyeri
White shrimp Penaeus setiferus
3-28
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Seasonal shellfish abundance near the Existing Site followed a
pattern similar to demersal fish abundance (Landy and Armstrong, 1980).
The number of individuals and mean biomass of captured macrocrustaceans
were highest in winter and lowest during summer.
Waters off central and western Louisiana shoreward of the 20 fm (36m)
isobath comprise one of the most heavily fished areas in the world
(Kutkuhn, 1966). In 1978 commercial fish and shellfish landings for
Louisiana central fishing district (which includes the Atchafalaya area)
were over 817 million pounds, or 48.8% of Louisiana total landings, and
valued at $90 million (NMFS, 1980b). The most valuable species caught
in waters off central Louisiana include penaeid shrimp (J?. setiferus and
aztecus), menhaden (Brevoortia patronus), several species of bottom
fish, blue crab (Callinectes sapidus), and oysters (Grassestrea
virginica).
Shrimp are caught throughout the shelf and in adjacent coastal
estuaries over clayey silt substrates (Barrett and Gillespie, 1973). The
offshore fishing grounds extend from the shoreline to the 50 fm (90m)
contour off Louisiana and comprise 15.3 million surface-acres (23,000
square miles). The inshore shrimp fishing ground extends from the
shoreline to the approximate northern boundary of the estuarine zone,
and contains 3.4 million surface-acres (5,300 square miles). Most of
the fishing for white shrimp occurs shoreward of the 14 fm (25m) depth
contour, from the Mississippi River to Freeport, Texas. Brown shrimp
grounds extend westward from Southwest Pass to the east coast of Texas
and Mexico, primarily in depths of 12 to 29 fm (22 to 52m) (Hildebrand,
1954). Greatest inshore catches of brown shrimp occur in the high
salinity waters of Breton Sound, Barataria, Caminada, and Timbalier
Bays. The greatest offshore brown shrimp catches are from the saline
nearshore waters south of Timbalier and Terrebonne Bays, while the
lowest cathes are in the low salinity waters near the Mississippi and
Atchafalaya Rivers. The largest white shrimp catches occur in areas off
western coastal Louisiana, coinciding with the high brown shrimp
production, but typically in less saline waters (Barrett and Gillespie,
3-29
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1973). The shrimp catch from inshore waters averaged 25.9 million
pounds per year, whereas the offshore waters averaged 31.3 million
pounds per year between 1967 and 1972 (Barrett and Gillespie, 1973).
The highest monthly inshore brown shrimp catch occurs in June, while the
largest offshore catch occurs in August. In contrast, the greatest
inshore and offshore catches of white shrimp occur in October (ibid.).
Temperature, salinity, and river discharge are environmental factors
which regulate the production of shrimp (Barrett and Gillespie, 1973).
"...[T]he greatest concern to future shrimp supplies are the long-range
effects of man-induced environmental changes in the estuaries" (DOE,
1981; pg. 1-16). Site-specific declines in shrimp productivity have
negligible impact on the total shrimp productivity because moderate
losses in the stock will be compensated for in adjacent areas (ibid.).
Menhaden (Brevcortia patronus) is the second most valuable fisheries
species, but represents the largest fishery in Louisiana waters in terms
of weight. Menhaden typically are caught in coastal estuaries and
waters shoreward of the 20 fm (36m) depth contour (DOE, 1981). In 1980,
the Gulf Menhaden catch was 1.55 billion pounds, of which 1.31 billion
pounds were taken from waters within 3 miles of the coast; the value of
the catch was $69.1 million (ibid.).
The states of Alabama, Mississippi, and Louisiana close the menhaden
fishery during winter months to protect the spawning stock. This
fishery has obtained or exceeded the maximum sustained yield, with the
restricted season probably the greatest factor preventing
over-exploitation (DOE, 1981).
3-30
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Large volumes of industrial or commercial fish are harvested from
shelf waters off Louisiana and processed for fish protein concentrate,
pet food, and fertilizer (Moore et al., 1970; Dunham, 1972). The
principal components of this fishery are Atlantic croaker (Micropogon
undulatus), longspine porgy (Stenotomus caprinus), sand seatrout
(Cynoscion arenarius) and sea catfish (Arius felis). The greatest
catches are made in winter and summer in depths of 7 to 40m (Moore et
al., 1970).
Other important fisheries resources include blue crabs and oysters,
both of which are harvested from coastal bays and estuaries (Bahr and
Hebrard, 1976; Van Sickle et al., 1976).
BENTHOS
Macrofaunal assemblages in Louisiana Shelf areas are composed of
euryhaline organisms characteristic of the open bay and mud bottom
habitats from Port Arkansas, Texas to Mobile, Alabama (Parker et al.,
1980). Polychaetes and, to a lesser extent, phoronids and pelecypods
generally are the most abundant macrofaunal groups, comprising
approximately 95% of the benthic population off Louisiana (Vfeissberg et
al., 1980).
Nearshore benthic organisms respond to seasonal changes in the
hydrological regime, especially to winter and summer pulses of dissolved
nutrients, which result in increases in plankton populations and
subsequent increases in food supply. Variability in the abundance and
composition of the benthos reflect seasonal changes in the nearshore
environment. In contrast, the offshore hydrographic regime is more
constant. Consequently, seasonal abundance patterns are less distinct
in offshore regions (Comiskey and Farmer, 1981).
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Macrofaunal assemblages near the Atchafalaya River ODMDS have been
examined during benthic investigations of several proposed salt dome
brine diffuser sites (Parker et al./ 1980; Weissberg et al., 1980a,b).
These studies characterized nearshore assemblages as typical of
estuarine areas. Communities were dominated by annual species, the
majority of which were polychaete worms (particularly Mediomastus,
Aglaophamus, Paraprionospio, Magelona, and Owenia), small molluscs
(Mulinia and Nassarius), and macrocrustaceans (shrimp and crabs). The
macrofaunal organisms consist mainly of deposit and suspension feeders;
however, omnivores and carnivores are also well represented (Parker et
al., 1980). The dominant organisms are small-bodied, opportunistic
species capable of rapid recolonization of disturbed sediments. Most of
these species complete their life cycle in a year or less. Recruitment
occurs during late autumn, winter, and early spring, allowing the larvae
of polychaetes and molluscs to settle before the onset of stressful
summer conditions which may be associated with low dissolved oxygen
concentrations and high water temperatures (Parker et al., 1980).
Population densities generally peak in late spring and early summer, and
later decline to the winter minimum (Parker et al., 1980; Weissberg et
al., 1980a,b).
Benthic communities along the Louisiana coast are susceptible to
periodic disturbances from storms. Tropical storm Debra passed through
a sampling station near the Existing .Site in August 1978 causing
considerable turbulence and sediment transport, and resulting in a
drastic reduction in the abundance of benthic infauna. Organisms such
as pericarid crustaceans and suspension feeding molluscs, that are
particularly sensitive to poor water quality were most effected (Parker
et al., 1980).
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Stations sampled by EPA/IEC in the vicinity of the Atchafalaya River
OEMDS were further inshore and shallower than the proposed brine
diffuser sites; however, the same general macrofaunal assemblage was
found, During both surveys polychaetes dominated the macrofauna,
particularly Medionastus californiensis, Paraprionospio pinnata, and
Cossura spp. During the December survey the Little surf clam Mulinia
lateral is was very abundant at a station west of the site probably as a
result of seasonal recruitment characteristic of this species (Parker et
al., 1980). By the following survey in late spring (May-June), _M.
lateralis was abundant only at a station within the site. Other common
members of this assemblage were the carnivorous ribbon worms
Cerebratulus cf. lacteus (and other unidentified rhynchocoela) and the
snail Nassarius acutus.
MAMMALS, REPTILES AND BIRDS
The diversity of marine mammals and reptiles is typically lower in
nearshore regions than in the adjacent offshore regions of the northern
Gulf (Bahr and Hebrard, 1976). Several migratory bird species utilize
nearshore areas for overwintering or breeding and nesting, whereas
offshore areas may be inhabited by strictly pelagic species.
Five species of turtles occur in the northern Gulf: green (Chelonia
mydas), Atlantic Ridley (Lepidochelys kempii), hawksbill (Eretmochelys
imbricata), leatherback (Dermochelys coriacea) and loggerhead Caretta
caretta (DOI, 1978). Feeding and nesting activities in the northcentral
Gulf off Louisiana have been reported only for the Atlantic Ridley.
Numerous species of whales and dolphins occur in the northern Gulf
(Table 3-11). The only species of marine mammal common to nearshore
waters is the Atlantic bottlenosed dolphin (Tursiops truncatus), which
occurs in the greatest numbers within tidal passes, and feeds on shrimp
and larger fish (Bahr and Hebrard, 1976). The greatest numbers of
mammals typically occur along the outer shelf and shelf-break. For
example, the short-finned pilot whale (Globicephala macrorhyncus), sperm
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TABLE 3-11
SPECIES OF MARINE MAMMALS KNOWN TO OCCUR IN THE GULF OF MEXICO
Common Name Scientific Name
Whales
Antillean-beaked Mesoplodon europaeus
Black right Balaena glacialis
Blue Balaenoptera musculus*
Bryde's B_. brydei
Cwaf t sperm Kogia simus
False killer Pseudorca cassidens .
Finback Balaenoptera physalus*
Goose-beaked Ziphius cavirostris
Humpback Megaptera novaeangliae*
Killer Orcinus orca
Minker Balaenoptera acutorostrata
Pygmy killer Feresa antenuata
Pygmy sperm Kogia breviceps
Sei Balaenoptera borealis*
Short-finned pilot Globicephala macrorhynchus
Sperm Physeter catodon*
Dolphins
Atlantic bottle-nosed Tursiops truncatus
Bridled Stenella frontalis
Gray's S._ coeruleoalba
Risso's Grampus griseus
Rough-toothed Steno bredanensis
Saddleback Delphinus delphis
Spinner Stenealla longirostris
Spotted S_. plagiodon
Pinnipeds
California sea lion Zalophus californianus
*Endangered species (Federal Register, 1979
Source: DOI 1977a
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whale (Physeter catodon), and Atlantic spotted dolphin (Stenella
plagiodon) are most common in outer shelf and open Gulf waters (DOE,
1978).
Several species of oceanic birds and waterfowl may occur throughout the
year in the nearshore region off Louisiana. Southern coastal Louisiana is
within the central north-south flyway and represents a stopping or over-
wintering grounds for a number of migratory species: blue and green
winged teal (Anas discors and A. carolinensis), widgeon (A. americana),
and canvasback (Aythya valisineria). Permanent residents of waters off
the Louisiana coast, including those of the vicinity of the Existing
OCMDS, may include frigatebirds (Fregata magnificens), gannets (Morus
bassanus), and Audubon's shearwaters (Puffinus Iherminieri). Densities of
"^. ^ ^^^
birds are seasonally variable, generally increasing from October through
December (DOE,'1978).
Bird populations further offshore may consist of pelagic species such
jaegers (Sterocoratius pomarinus and S. parasiticus), shearwaters
(Puffinus griseus and P. Iherminieri), and frigatebirds (F_. magnificens).
THREATENED AND ENDANGERED SPECIES
Six species of endangered marine mammals have been sighted in the
northern Gulf of Mexico (Table 3-12). Most were chance sightings and do
not indicate the presence of indigenous populations (DOI, 1977). All of
the endangered marine mammals are rare in the northern Gulf of Mexico
(ibid), and not expected to commonly occur at the Existing Site.
Several threatened or endangered species of marine reptiles occur in
the northern Gulf of Mexico (Table 3-12). The Atlantic Ridley and
leatherback turtles may occur as transients at the Existing Sites.
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as
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TABLE 3-12
ENDANGERED AND THREATENED MARINE MAMMAL
AND REPTILE SPECIES AND CRITICAL HABITATS
Louisiana: Gulf of Mexico
Listed Species
Scientific Name
Status Date Listed
MAMMALS
fin whale
humpback whale
right whale
sei whale
sperm whale
blue whale
Balaenoptera physalus
Megaptera novaeangliae
Eubaleana glacialis
Balaenoptera borealis
Physeter catodon
Balaenoptera musculus
E
E
E
E
E
E
12/2/70
12/2/70
12/2/70
12/2/70
12/2/70
12/2/70
REPTILES
green sea turtle
hawksbill sea turtle
Kemp's (Atlantic)
ridley sea turtle
leatherback sea
turle
loggerhead sea
Chelonia mydas
Eretmochelys imbricata
Lepidochelys kempi
Dermochelys coriacea
Caretta caretta
E
E
E
E
Th
7/28/78
6/02/70
12/02/70
6/02/70
7/28/78
SPECIES PROPOSED FOR LISTING
None
CRITICAL HABITAT
None
CRITICAL HABITAT PROPOSED LISTING
None
Source: Charles A. Oravetz; Southeast Region, National Marine Fisheries
Service Letter 10/18/83
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Endangered brown pelicans Pelecanus occidentalis nest along the
Louisiana shoreline. The native populations in Louisiana was extirpated
in 1962 by poisoning from the pesticide endrin (Schreiber, 1980). A
colony of brown pelicans, introduced from Florida, presently exists at
Queen Bess Island (Schreiber, 1980; Blus et al., 1979).
Some threatened or endangered species may occur as transients at the
Atchafalaya OCMDS. The Existing Site is small in relation to their
total ranging areas and dredged material disposal at the site is not
expected to affect any of the threatened or endangered species.
GENERAL RECREATION
\
Coastal regions off Louisiana are extensively used for recreational
activities, including fishing, swimming, pleasure boating, beachcombing,
and diving. In addition, camping, picnicking, and hunting occur along
the shore. The Atchafalaya OCMDS is relatively close to shore;
therefore, some recreational activities (boating, fishing, and diving)
may occur within or near the site. Beachcombing, swimming, camping, and
hunting activities are restricted to the immediate shore.
NAVIGATION
The dredged channel is used for navigation; dredging is necessary to
keep the channel open. The volume of shipping in the Atchafalaya River
Bar Channel has decreased from 4,786,737 tons in 1973 to 3,601,216 tons
in 1978 (CE, 1979). Ship traffic using the channel consists primarily
of oil field supply boats, offshore tugs, fishing boats, and barges.
The majority of shipping is internal, within the area between Morgan
City and the 20 ft. Gulf contour (ibid.). The vessel traffic travels
primarily to Morgan City or eastward to an industrial complex on Bayou
Chene. Major commodities shipped through the channel are menhaden,
marine shells (unmanufactured), crude petroleum, clay, basic chemicals,
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distillate fuel oil, building cement, iron and steel pipe, miscellaneous
manufactured products, and water (CE, 1979).
OIL AND GAS
Immense oil and gas reserves are contained within shelf and
shelf-break regions off Louisiana. By the early 80's, 482 fields
discovered in the northern Gulf had produced 5 billion barrels of oil
and 48.7 trillion cubic feet of gas (Havran, 1981). Reserves in the
western Gulf (west of the Mississippi Delta) contain an estimated 2.8
billion barrels of oil and 42.9 trillion cubic feet of gas on the
shelf.
Extensive oil and gas development occurs off the Atchafalaya area.
Within three areas off Atchafalaya Bay, i.e., South Marsh Island, Eugene
Island, and Ship Shoal, 26.9% of Louisiana's oil and gas fields occur.
A portion of the Existing Site is located within leased blocks, and one
platform is located in the southern corner of the Site (Offshore, 1982;
DOC, 1980a).
MARINE SANCTUARIES
No marine sanctuaries occur in the immediate vicinity of the Existing
Site. Shell Keys and Marsh Island Wildlife refuges are approximately 25
nmi, west of the Existing Site. Fishnet Bank, the closest protected
Area of Biological Significance, is approximately 90 nmi south of the
Existing Site.
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Chapter 4
ENVIROTO1ENTAL
Effects of dredged material disposal, described in this chapter, are
classified under two broad categories: (1) ecosystem and (2) public
health and safety. The ecosystem section describes the environmental
effects of dredged material disposal on water and sediment quality, and
the biota. The public health and safety section discusses commercial
fisheries, potential contamination of edible fish, development of
nuisance species, and effects on navigation and aesthetics. Unavoidable
adverse environmental effects and mitigating measures, short-term use
versus long-term productivity, and irreversible and irretrievable
\
commitments of resources also are discussed.
EFFECTS ON THE MARINE ECOSYSTEM
Short-Term and Long-Term Effects
Specific Long-term effects of dumping at the Atchafalaya ODMDS were
not studied during the CE's Dredged Material Research Program (DMRP);
however, specific short-term studies (during dumping) of nutrient and
dissolved and particulate trace metal concentrations were conducted at
the Existing Site (Schubel et al., 1978). The results of the DMRP
Aquatic Field Investigation Studies provide insight regarding the effects
of dredged material disposal; however, they must be applied carefully
when predicting impacts, because local conditions affecting the fate and
effects of impacts may vary from site to site depending on the
composition of the dredged materials and the physical and biological
characteristics of the disposal site. Chemical, geological, and
biological oceanographic data were collected at the Existing Site during
4-1
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EPA/IEC surveys to assess the effects of dredged material disposal on the
marine environment, and determine whether any adverse effects of dredged
material disposal identified within the Site were detectable outside the
site boundaries.
Water Quality
Disposal of dredged material should not appreciably degrade water
quality in regions adjacent to the Atchafalaya OCMDS. In general,
changes in water quality associated with dumping are relatively
short-term, and conditions return to normal within a period of minutes to
hours. Results of several long-tern studies at nearshore locations,
summarized by Brannon (1978), indicate that dredged materials have
limited chronic impacts on the water quality of the disposal site.
TURBIDITY
Dredged material disposal results in a temporary increase of turbidity
levels and suspended solid concentrations in the water column (CE, 1980).
The duration of a turbidity plume will depend on particle size and
density, currents, and turbulent mixing (Wright, 1978). Dredged
materials from the Atchafalaya Bar Channel contain appreciable quantities
of fines (94 to 98%) which may remain suspended for periods of minutes to
hours. Wright (1978, p. 48) concluded that at most dredged material
disposal sites, increases in turbidity persisted for only a few hours
and, in addition, "...storms, river discharge and other natural phenomena
resulted in turbidity increases of much greater magnitude than those
associated with disposal."
Studies conducted at the Atchafalaya ODMDS during dredged material
disposal noted that turbidity plumes were of limited duration and areal
4-2
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extent (Heaton, 1978; Schubel et al., 1978). Concentrations of suspended
sediments are lower in the offshore waters.
NUTRIENTS
Resolubilization of nutrients is cannon from both polluted and
nonpolluted sediments dredged from coastal areas (Windom, 1976). Results
of elutriate tests (Table 4-1) performed on dredged materials from the
Atchafalaya Bay Channel demonstrated releases of soluble organic nitrogen
(total Kjeldahl nitrogen [TKN]) and carbon (CE, 1978).
Releases of nitrogen, especially ammonia, are common from dredged
materials (Windom, 1975). Coastal waters are characteristically limited
with respect to nitrogen (Ryther and Dunstan, 1971); therefore,"localized
releases may temporarily stimulate phytoplankton productivity (ibid.).
Elevated concentrations of ammonia, sufficient to cause toxicity to
aquatic organisms, at the disposal site or adjacent areas are unlikely
(Brannon, 1978). Increased anmonia concentrations in the water column
are ephemeral, and subsequent decreases result from rapid dilution and
mixing (Wright, 1978).
Localized increases in phosphorus concentrations following dumping are
typically of short duration due to rapid adsorption onto suspended
particulate matter, particularly clay particles (Wright, 1978; Windom,
1975). Chronic water quality problems resulting from long-term leaching
of nutrients from dredged sediments are not expected (Rrannon et al.,
1978).
Studies conducted at the Atchafalaya ODMDS measured releases of
ammonium and silicate species during dredged material disposal, however,
concentrations were quickly diluted to background levels. Dissolved
orthophosphate, ammonia, and silicate levels were not effected by
disposal (Schubel et al., 1978; Heaton, 1978).
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TABLE 4-1
ELUTRIATE TEST RESULTS FOR
ATCHAFAIAYA BAR CHANNEL DREDGED MATERIAL*
Source: CE, 1978
As
Be
Cd
Cr
Cu
Pb
Mn
Hg
Ni
Se
V
Zn
Cyanide (mg/1)
Phenol
COD (mg/1)
TKN (mg/1)
Elutriate Test
4-7
<0.5
<0.5
3-8
3-4
6-9
1900-3100
<0.05
3-5
<0.5
<0.05
<0.5-10
<0.005
<0.5
45-90
3.0-3.7
Native Water
2-4
<0.5
<0.5
<10
2-4
3-6
30-50
<0.05
2-10
<0.5
NM
<0.5-20
<0.005
<0.5
NM
NM
*Concentrations in ug/1 unless otherwise stated.
NM = Not measured
DISSOLVED OXYGEN
Materials with potential oxygen demands are generally present in
dredged material. Their release following disposal imposes both a
chemical and biological oxygen demand (COD and BOD) on the water column.
4-4
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However, Schubel et al., (1978) showed that the effects of adding oxygen
demanding material to the water column are functions of the length of
time the material resides in the water column and the amount of water
available for dilution. In shallow water, such as the Atchafalaya ODMDS,
approximately 95-99% of the dredged material is deposited close to the
discharge source and within several minutes after release. The remaining
1-5% of the dredged material is deposited within a few hours after
discharge (ibid.). Only a small percentage of the oxidizable components
in dredged material is reactive on a time-scale comparable to the
settling rate of the majority of the discharged particulate matter. The
reduced forms of sulfur, iron, and manganeses present in sediment
interstitial waters place an immediate oxygen-demand on the water column.
The organic matter and sulfide minerals present in the dredged sediments
also exert an oxygen-demand, but on a longer time scale. Most of the
decomposition of organic matter is accomplished by bacterial degradation;
oxidation of sulfide minerals is generally limited to surficial sediment
layers. Once the dredged material is deposited, the oxygen demand on the
overlying waters is dependent on the expulsion of interstitial water
during compaction and, thereafter, is diffusion-limited (ibid.).
TRACE METALS
Nearshore sediments are a major sink for riverine and anthropogenic
trace metals (Trefry, 1977). Sediments dredged from river mouths and
coastal navigation channels therefore may contain levels of trace metals
which are elevated relative to coastal abundance (Holmes, 1973).
However, releases of trace metals from sediments, and subsequent changes
in disposal site water quality, cannot be predicted solely on the basis
of bulk chemical analysis of the dredged sediments (Windom, 1975; Brannon
et al., 1978). For example, results of the DMRP (Brannon, 1978) and
studies by Windom (1975, 1976) demonstrate that following dumping, the
concentrations of certain dissolved metals (e.g., Zn, Cu, Od, and Pb) in
disposal site waters may be regulated by adsorption onto insoluble iron
ox ides.
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Studies at the Atchafalaya ODMDS (Schubel et al., 1978; Heaton, 1978)
found no well-defined plume of dissolved trace metals during dredged
material disposal, and no linear relationship between dissolved and
particulate trace metals. A few anomolously high levels of Mn were
observed, however, these were associated with high TSS concentrations
(approximately 1000 mg/1) near the discharge point. Concentrations of
dissolved Zn, Cu, Cr, Cd, and Pb were low (usually below detection
levels) throughout the Atchafalaya sampling area; comparisons between
concentrations in the dredged material plume and in unaffected water
showed no apparent differences. Therefore, it may be concluded that no
substantial release of these metals occurred during dredged material
disposal (Schubel et. al., 1978; Heaton, 1978).
Long-term solubilization of trace metals from dredged materials is
minimal, and too small to produce significant adverse impacts to water
quality (Brannon, 1978; Windom, 1975, 1976). For example, surveys
conducted by EPA/IEC found the greatest particulate trace metal
concentrations were associated with highest TSS concentrations.
Dissolved trace metals exhibited an inverse relationship with TSS and
particulate trace metal concentration which may be caused by scavenging
of metals from solution onto sediment particulates (ibid.). Dissolved Mn
and Pb levels varied widely throughout the survey area, however,
concentrations were comparable to those from previous studies. Total
(particulate plus dissolved) trace metal concentrations were below their
respective EPA minimum marine water quality criteria (45 FR 79318 et
sq.)
Elutriate tests are intended to indicate the potential for release of
dissolved trace metals from dredged sediment when mixed with seawater.
Elutriate tests (Table 4-1) conducted by CE (1978) on the dredged
material from the Atchafalaya Bar Channel indicated little or no release
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of trace metals, except for Mn, which is generally released in the
elutriate test (Brannon, 1978; Heaton, 1978). EPA/IEC conducted
elutriate tests on sediments outside and within the Atchafalaya ODMDS.
Except for zinc, which showed a slight release, results were similar to
those of CE (1978). Metal released from sediments within and outside the
OCMDS were similar.
HYDROCARBONS
Synthetic organics, such as pesticides and polychlorinated biphenyls
(PCBs) do not occur naturally in sediments, but result from anthropogenic
contamination (Brannon, 1978). Chlorinated hydrocarbons (CHCs) have low
water solubility, are rapidly sorbed to sediments, and only small
quantities are released to interstitial waters (Burks and Engler, 1978).
Concentrations of pesticides and PCBs in waters overlying the
Atchafalaya ODMDS immediately following dumping have not been measured.
However, EPA/IEC surveys within and around the Existing Site found most
dissolved CHC levels in the water column to be below detectable limits;
only dieldrin, the DDT derivative pp'DDE, and the PCB Arochlor 1254 were
present in measurable quantities. All concentrations were below their
respective EPA single measurement criterion (45 FR 79318 et seq/).
SEDIMENT QUALITY
Nearshore surficial sediments in the Atchafalaya region are affected
by outflow from the Atchafalaya River, currents, and wave action. An
estimated 53 million m^/yr of fine-grained sediment, along with
associated contaminants, are carried from Atchafalaya Bay and deposited
on the western Louisiana shelf (Walls et al., 1981). These sediments are
deposited in the channel, as well as in the ODMDS, resulting in similar
grain size and chemical composition between the dredged material and
ODMDS sediments.
4-7
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Sediments within and around the Atchafalaya ODMDS are predoninantely
composed of silts and clays (82 to 99% fines) and similar in composition
to the dredged material (94 to 98% fines) (CE, 1978). Clay content
within the Existing ODMDS was lower during th EPA/IEC December survey
than during the May/June surveys, illustrating the winnowing of the finer
particles during winter. Since the dredged material is similar to the
disposal site sediments, and sediment transport is known to occur in the
area, long-term or persistent changes in grain-size at the ODMDS
resulting from dredged material disposal should be negligable.
CHEMICAL COMPOSITION
Contaminants in dredged material are generally not released into the
water following disposal, but remain associated with the sediments
(Brannon, 1978). The greater proportion of the sediment trace metals and
hydrocarbons will be associated with the mobile silt and clay fractions
(Chen et al., 1976). Therefore, the extent of changes in the chemical
compositon of the sediments depends on the persistence of the fine
fractions within site boundaries. As stated previously, the Atchafalaya
ODMDS is located in a dynamic area. Consequently, measurable long-term
alterations or accumulations of contaminants in disposal site sediments
are unlikely. Trace metal levels measured during EPA/IEC surveys within
and around the ODMDS were similar during winter and spring, and exhibited
no consistant spatial or temporal trends. The levels, including the
relatively high levels of As, were also comparable to previously reported
values for the nearshore region (Weissberg et al., 1980; CE, 1978).
Chlorinated hydrocarbon concentration in sediments were low or
non-detectable during EPA/IEC surveys. No effects of dredged material
disposal on sediment parameters could be identified at the ODMDS.
BIOTA
In general, the disposal of dredged material presents four potential
problems to aguatic organisms: (1) temporary increases in turbidity, (2)
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changes in physical or chemical characteristics of the habitat, (3)
smothering by burial, and (4) introduction of pollutants (Hirsch et al.,
1978). The magnitude of adverse impacts on the existing fauna depends on
the similarity of the dredged sediments to existing sediments, frequency
of disposal, thickness of the overburden, types of organisms affected,
and physical characteristics of the habitat (Pequegnat et al., 1978). It
is often difficult to distinguish adverse effects caused by sediment
disposal from changes due to natural variability in habitat or species
abundances.
PLANKTON
Effects of dredged material disposal on plankton are difficult to
assess because of the high natural variability of populations. The
influences of tidal and river discharges, as well as diel changes in
zooplankton abundances, increase the difficulty of detecting disposal
effects. Sullivan and Hancock (1977) concluded that for most oceanic
areas natural plankton fluctuations are so large that field surveys would
not be useful for detecting the impacts of dredged material disposal.
Disposal of dredged material creates a temporary turbidity plume
consisting of the fine-grained silt and clay. Entrainment of
phytoplankton, zooplankton, and ichthyoplankton within a turbidity plume
has a potential for localized plankton mortality by exposure to decreased
light transmittance, and prolonged exposure to suspended particulates and
released contaminants (Wright, 1978). Elevated suspended particle
concentrations may inhibit filter-feeding planktonic organisms, although
the extent of this impact is unknown.
Changes in water quality following disposal are temporary, thus
chronic exposure of organisms to trace contaminants is not expected.
Winter bioassay test results with representative zooplankton species
(Artemia salina) demonstrated no significant mortality in the liquid or
suspended phase (Drawas et al., 1979b); summer tests were inconclusive
(Drawas et al ., 1979a).
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BENTHOS
Benthic organisms at the Atchafalaya ODMDS are exposed to increased
suspended sediment concentrations, burial, and temporary reduction in
water quality. The immediate effects of disposal on infauna at the ODMDS
have not been investigated. The following discussion of potential
impacts on the benthos is based on the results of the DMRP (summarized by
Wright, 1978 and Hirsch et al., 1978), site specific infaunal data
collected during EPA/IEC surveys, and bioassay and bioaccumulation tests
(Drawas et al., 1979a,b).
Significant adverse impacts to marine organisms are not expected from
uncontarninated or lightly contaminated particulates (Hirsch et al.,
1978). No significant adverse impacts to benthic organisms, due to
changes in water or sediment quality were detected during the DMPP
(ibid.). Water quality changes resulting from dumping are short-term; no
evidence of persistent alterations "of water quality at the disposal site
or adjacent waters were detected during EPA/IEC surveys.
Summer bioassay tests of dredged material from the Atchafalaya Bar
Channel were inconclusive (Drawas et al., 1979a). No significant
mortality to benthic organisms occurred in the liquid or suspended parti-
culate phases of winter bioassay tests (Drawas et al., 1979b). Bioaccu-
mulation of trace metals and hydrocarbons in representative benthic
organsims was detected; however, for most organisms, concentrations were
below FDA action levels during the winter bioaccumulation tests. The
maximum mean mercury concentration in tissues of the bivalve mercenaria
jp_ exceeded FDA action levels during the winter bioaccumulation tests.
The observed mercury levels were thought to result from the low biomass
of the test organisms and a heterogenous distribution of mercury within
the sediments (ibid.). All concentrations of trace metals and CHCs
reported for summer bioaccumulation tests were below FDA action levels
(Drawas et a., 1979a).
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Direct effects (i.e., burial of organisms) are restricted to the
inmediate areas of the disposal sites (Hirsch et al., 1978). Previous
investigations of the effects of burial of benthic infauna demonstrated
that adverse impacts are typically limited to non-rootile species
(Richardson et al., 1977). Active or motile species are capable of
burrowing up through at least 32 cm of overburden (Mauer et al., 1978).
Nevertheless, dredged material disposal at an ODMDS will likely smother
some epifaunal and infaunal organisms. Consequently, densities and
diversity will temporarily decline (CE, 1978). However, benthic
assemblages in the northern Gulf experience high natural variability in
abundances and diversity due to seasonal changes in adult mortality and
larval recruitment rates (Parker et al., 1980).
Recently deposited sediment will be recolonized by motile infaunal
organisms burrowing up through the overburden, by species migrating from
adjacent undisturbed areas, and by recruitment of larvae and juvenile
forms (Hirsch et al., 1978). Specific recolonization patterns will be
influenced by the composition of the new sediment and adjacent benthic
communities (Oliver et., 1977).
During EPA/IEC surveys, the macrofaunal assemblages within and around
the Atchafalaya ODMDS were characteristic of the general region and
dominated by polychaetes. Many of the dominant organisms were
small-bodied, opportunistic species capable of rapid recolonization of
disturbed sediments. Large macroinvertebrates (mainly shrimp and crab)
were also common throughout the area. No effects due to disposal were
found at the ODMDS.
The consequences of temporarily disrupting the benthic contnunity
within the disposal site cannot be easily evaluated (Wright, 1978).
Hirsch et al. (1978; p.17) concluded that "the more naturally variable
the environment, the less effect dredging and disposal will have, because
animals and plants common to the unstable areas are adapted to stressful
conditions and have life cycles which allow them to withstand the
4-11
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stresses imposed by dredging and disposal. Habitat disruption can also
be minimized by matching the physical characteristics of the dredged
materials to the substrate found at the disposal site." The Atchafalaya
OCMDS is located in a naturally-disturbed nearshore environment, and the
dredged sediment is physically similar to the OCMDS sediments.
Therefore, short-term alterations of the habitat and adverse impacts on
the biota within and adjacent to the Site will be minimized. Because of
the dynamic nature of the environment, and the apparent absence of
significant adverse effects on water or sediment quality, it is unlikely
that previous disposal activity at the OCMDS has measurably altered the
benthic habitat.
NEKTON
Data sufficient to characterize the effects of dredged material
disposal on nekton inhabiting the Atchafalaya ODMDS are unavailable.
DMRP results (Wright, 1978) suggest that fish usually are not directly
affected by dredged material disposal. The mobility of nektonic
organisms generally precludes adverse effects due to sediment inundation.
Summer series bioassay tests on nekton species were inconclusive
(Drawas et al ., 1979b). Winter bioassay tests using nekton species
detected no significant mortality for the liquid phase. However,
significant mortality to Cyprinodon occurred in the 100% test medium for
the suspended particulate phase (ibid.). Bioaccumulation of trace metals
and hydrocarbons occurred in summer and winter tests, however, summer
test concentrations w°re below FDA action levels (Drawas et al., 1979a).
In winter bioaccumulation tests, maximum mean mercury concentration in
tissues of the shrimp Paleomonetes exceeded FDA action levels. The
observed mercury levels may have been the result of low bicmass samples
and a heterogenous distribution of mercury within the sediments (Drawas
et al., 1979b).
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Localized burial of benthic fauna may decrease the abundance of fish
prey items, causing temporary declines in finfish abundances and
f
diversity at the disposal site. Results of the DMRP studies assessing
the effects of dredging on demersal fish were ambiguous. Wright (1978)
reported that in some cases relatively higher numbers of fish occurred at
an OEMDS after disposal. In other cases, short-term avoidance of
disposal sites by finfish were observed after dumping. Wright (1978, p.
50) concluded "Some question exists as to whether this behavior
represented avoidance of the (dredged) material or was the result of
normal seasonality and the sampling techniques that were used."
No unique nekton habitats or spawning areas occur within the
Atchafalaya ODMDS. Adverse effects on nekton resulting from intermittent
and localized disposal operations at the Site would be negligible.
MAMMALS AND REPTILES
Specific effects of dredged material disposal on marine mammals and
reptiles have not been studied. Because of their relatively large size
and the mobility of most species, direct impacts should be negligible at
the Atchafalaya ODMDS. In addition, the Site represents only a small
portion of the total range of the mammal and reptile species occurring in
the northcentral Gulf of Mexico. Dumping would not occur in
geographically restricted feeding, breeding, or passage areas of any
mammal, bird, or reptile species.
THREATENED AND ENDANGERED SPECIES
Infrequent and localized disposal at the Atchafalaya ODMDS would have
no adverse impacts on the food source, migratory passage or breeding
areas of endangered whales, birds, or turtles. A brown pelican colony is
located at Queen Bess Island, Louisiana, 65 nmi east of the Atchafalaya
area. Potentials for chlorinated hydrocarbons (especially dieldrin and
endrin; c.f., Blus et al., 1979) desorbing from dredged materials and
accumulating in food sources of brown pelicans are unknown.
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Summary of Effects on the Ecosystem
Potential impacts associated with dumping at the Atchafalaya ODMDS may
include burial of benthic infauna, temporary releases of nutrients and
trace metals, formation of a temporary turbidity plume, and temporary
depression of dissolve oxygen concentrations. Physical habitat
disruptions resulting from disposal operations are minimized at sites
having naturally variable or unstable substrates, and where" dredged
sediments are similar to disposal site sediments. Continual riverine
inputs and resuspension by waves and periodic storm-induced turbulence at
the OCMDS will redistribute dredged sediments and adjacent sediments;
thus precluding permanent alteration of the substrate. Cumulative or
long-term impacts on the ecosystem due to dumping would therefore be
unlikely.
PUBLIC HEALTH AND SAFETY
Ensuring that public health and safety are not adversely affected by
ocean disposal of dredged materials is a primary concern. Health hazards
may arise if the chemical nature of the material has the potential for
bioaccumulation of toxic substances in organisms. Potential impacts on
human health can be inferred from bioassay and bioaccumulation tests
performed on marine animals. The results of these tests performed on the
Atchafalaya Bar Channel dredged materials (discussed earlier in this
chapter) do not indicate any potential human health hazards.
Fisheries
Nearshore areas of the northern Gulf of Mexico support one of the most
productive fisheries in the United States for shrimp, menhaden, and
bottom fish including croaker, drum, and sea trout. Coastal areas with
sand/silt substrates including the Atchafalaya ODMDS are used seasonally
by many commercial species for feeding, breeding, and passage activities;
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however, none of these activities are unique or restricted to the Site.
Fishing activities for demersal and pelagic fish and shrimp extend
throughout nearshore and shelf regions. Fishing occurs throughout the
year but most activity occurs from March through October (Dugas,
1981*). Consequently, some interferences with commercial fishing and
fisheries resources from dredged material disposal in nearshore regions
are inevitable. The Atchafalaya ODMDS represents only a small portion of
the total fishing grounds of the northern Gulf of Mexico. Any adverse
effects are likely to be restricted to the disposal site. Therefore,
dredged material disposal will potentially affect only a small percentage
of this resource (e.g., DOE, 1981).
Tests of sediments dredged from the Atchafalaya Bar Channel demon-
strated no significant bioaccumulation of trace metals or hydrocarbons in
tissues of the shrimp Paleomonetes (Drawas et al., 1979a,b). Two species
of penaeid shrimp collected within and around the ODMDS during the
EPA/IEC surveys had low trace metal concentrations, and mercury
concentrations were below FDA action/tolerance levels for edible marine
organisms. One species of shrimp and one species of crab collected
during the surveys had low quantities of dieldrin, pp'DDE, and PCB
(Aroclor 1254); however, concentrations were well below FDA
action/tolerance levels for edible marine organisms.
Navigation
The disposal of dredged materials could present two potential hazards
to navigation: (1) mounding within the disposal site, and (2) inter-
ference of the dredge and/or pipeline with vessel traffic.
Mounding and/or shoaling may temporarily occur within the Atchafalaya
ODMDS following dumping. NOS charts of the Atchafalaya area indicate
long term shoaling has not occurred in the Existing Site (DOC, 1980a).
*Donald J. Dugas, Louisiana Department of Wildlife and Fisheries, Seafood
Division, personal communication.
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The pipeline dredges used for maintenance work at the Atchafalaya
ODMDS may temporarily interfere with some shipping traffic by blocking
sections of the channel. Barges or hopper dredges, if required, may also
create interferences with shipping traffic in the Atchafalaya Bar
Channel.
Aesthetics
Dredged material disposal at the Atchafalaya ODMDS will create a
temporary turbidity plume. The plume would not be visable from shore,
and would disperse after dumping ceases. The additional discoloration of
naturally turbid waters will be minor. No excessive noises or odors are
expected.
Sunmary of Effects on Public Health and Safety
Previous dumping at the Atchafalaya ODMDS has caused no detectable
impacts on public health and safety. No shoaling or degradation of
fisheries resources or aesthetics have been reported.
Limited potential exists for bioaccumulation of metals and
hydrocarbons in shrimp or fish tissue as a result of exposure to dredged
materials (Drawas et al., 1979a,b). However, exposure to transient
species is typically of short duration; thus, potential harm to humans
consuming locally caught seafood is low (ibid.).
UNAVOIDABLE ADVERSE
ENVIRONMENTAL EFFECTS AND MITIGATING MEASURES
In general, few significant adverse impacts result from dredged
material disposal (Wright, 1978). Increases in turbidity, releases of
nutrients or trace metals, and reductions of benthic faunal abundances
and diversity are short-term effects which would occur. Results of the
DMRP (Hirsch et al., 1978) indicate that impacts within the site are
4-16
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minimized when dumping occurs in naturally variable, high-energy
environments. The Atchafalaya ODMDS is situated in a dynamic, nearshore
environment, thus long-term or cumulative impacts will be minimal, and
additional mitigating measures should be unnecessary. Results of EPA/IEC
surveys at the Atchafalaya ODMDS suggest that previous dumping has not
caused significant degradation of the water or sediment quality, or
persistent changes in the composition of the fauna in areas adjacent to
the ODMDS.
Limited interferences with nearshore fisheries may occur from dumping.
The Atchafalaya ODMDS is located within passage areas of nekton that
seasonally migrate to and from the estuaries, bays, and Gulf during
various stages of their life cycle. Dredging and disposal could be
restricted to periods of the year when these migrations are diminished or
periods of greater turbulence (i.e., more rapid sediment dispersion).
However, the ODMDS represents only a small percentage of the total
nearshore fishing grounds. Therefore, mitigating measures to reduce
interferences with commercial or recreational fishing are not warranted.
RELATIONSHIP BETWEEN
SHORT-TERM USES AND LONG TERM PRODUCTIVITY
Long-term degradation of water or sediment quality, which might
decrease the long-term productivity or value of resources, has not been
detected within or adjacent to the Atchafalaya ODMDS. Commercial fishing
and sportfishing, at and near the Site, should not be significantly
impaired because the Site constitutes a small percentage of the total
fishing grounds.
Adverse effects on the productivity of the nearshore region adjacent
to the ODMDS due to localized and intermittent disposal activities, are
considered negligible in comparison to the economic benefits derived from
maintaining the Atchafalaya Bar Channel (CE, 1978).
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IRREVERSIBLE OR
IRRETRIEVABLE COMMITMENTS OF RESOURCES
Irreversible or irretrievable resources committed to the proposed
action of final designation of the Atchafalaya ODMDS include:
1. Energy resources will be used as fuel for dredges, pumps,
and disposal vessels.
2. Economic resources will be committed to the costs of ocean
disposal.
3. Benthic organisms will be buried by dredged material upon
disposal.
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Chapter 5
COORDINATION
This Draft EIS was prepared by William C. Shilling, P.E.f Chief, and Janis
Jeffers, Environmental Protection Specialist of the Ocean Dumping EIS Task Force.
It is based on information prepared for EPA under contract by Interstate
Electronics Corporation. Support in preparation of the Draft was provided by
Edith R. Young. The Preliminary EIS has undergone internal review by EPA and the
Corps of Engineers.
Endangered Species Act of 1973
Section 7 Coordination
Formal coordination has been initiated by letter to the Washington, D.C.
National Marine Fisheries Service office and U.S. Fish and Wildlife Service
office.
Coastal Zone Management Act
Federal Consistency Evaluation
The State of Louisiana, Department of Natural Resources, has been contacted
and requested to provide this office with the elements of their State Coastal
Zone Management Program which are applicable to the Atchafalaya ODMDS designation
EIS consistency evaluation. They have responded by identifying the sections of
the Louisiana Coastal Resources Program that are the basis for consistency review
in Louisiana. An evaluation of consistency as it pertains to these sections, is
summarized in Table 5-1.
5-1
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Table 5-1
CONSISTENCY EVALUATION
Louisiana State and Local
Coastal Resource Management
Act
§213.2 Declaration of
Public Policy
Evaluation
§213.10 Special Areas and
Projects
Coastal Use Guidelines
(1) Guidelines Applicable
to all uses
Protection of Louisiana's coastal resources
(policy 1) will be enhanced by designation of an
Ocean Dredged Material Disposal Site (ODMDS).
Site designation limits the effects of dredged
material disposal to one ocean location in the
area while facilitating maintenance of the channel
for shipping uses. Multiple use of the coastal
zone (policy 3) will not be affected and is
addressed in Chapter 2 of the EIS (Specific
criteria 228.6(9)). Dredged material disposal
will not interfere with recreational use of the
coastal zone (policy 6) as noted in Specific
criteria 228.6{a)(3) and (8) in chapter 2 of the
EIS.
The locations of areas of biological significance
were considered in the EIS evaluation (General
criteria 228.5(b); Specific criteria
228.6(a)(8)(ll)).
Possible adverse impacts (1.7) of site Designation
were identified and discussed in Chapter 4 of the
EIS. Evaluation of the site for final designation
is based on the Ocean Dumping Regulations issued
pursuant to the Marine Protection, Research, and
Sanctuaries Act of 1972 (86 Stat. 1052), as
amended (33 U.S.C.A. §1401, et. seq.). The Act
requires that "dumping will not unreasonably
degrade or endanger human health, welfare, or
amenities, or the marine environments, or economic
potentialities" §102(a). Future use of the site
would be controlled through the permitting process
in conformance with applicable regulations. Other
uses for the dredged material were not evaluated
in the EIS since that determination is appropriate
in the project planning and permitting stages
(1.6.).
5-2
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Table 5-1 (Gont'd)
(3) Guidelines for Linear
Facilities
(4) Guidelines for Dredged
Spoil Deposition
(5) Guidelines for Shore-
line Modification
(7) Hydrologic and Sediment
Transport Modifications
Comments
Although linear in configuration, the ODMDS
is not a permanent linear structure. The
dredged materials disposed within the site
form a temporary mound which will be
redistributed through littoral processes.
The alignment of the ODMDS corresponds to
the historically used site (3.5). The ODMDS
parallels and is adjacent to the channel
which will be the primary source of dredged
material. The dredged material is similar
in composition and size to the material in
the site and is not suitable for fill. The
site is not located in a wetland or
estuarine area (3.2), nor does it traverse
or intersect a barrier island (3.7), beach,
tidal pass, reef or other natural gulf
shoreline (3.8). Historical use of the
ODMDS has not resulted in reports of the
disruption of natural hydrologic and
sediment transport patterns, sheet flow or
water quality (3.9).
The site is located in an historically used
dredged material disposal area. The
evaluation summarized in the EIS resulted in
a determination that there was no
environmental advantage to alternative ocean
sites. Upland disposal was not ruled out,
but the comparative suitability should be
determined in the permitting process (4.2).
The ODMDS will not adversely affect
wetlands, the oyster reefs, or submerged
vegetation (4.3, 4.4). Effects on
navigation and fishing (4.5) are addressed
in Chapter 4 of the EIS.
Designation of an ODMDS is not intended to
directly or indirectly change or prevent
change to the shoreline (Guideline
Definition; examples include bulkheading,
piers, docks, and jetties).
The ODMDS is not intended to change water
circulation, direction of flow, velocity,
level, or quality or quantity of transported
sediment (Guideline Definition, examples
include locks, impoundments, dams and
canals.
5-3
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Chapter 6
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6-5
-------
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6-8
-------
REFERENCES (Cont'd)
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6-9
-------
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6-10
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i
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6-11
-------
Appendix A
REPORT OF FIELD SURVEY
PREFACE
Interstate Electronics Corporation (IEC), under contract to the Environ-
mental Protection Agency (EPA), Contract No. 68-01-4610, conducted two surveys
of the Atchafalaya River Ocean Dredged Material Disposal Site (ODMDS). The
survey plans were prepared by IEC and submitted to EPA in November 1980 and
May 1981. The 1980 plan was approved by T. A. Wastler and the 1981 plan by
W. C. Schilling (Chiefs, Marine Protection Branch, EPA). Field work was
conducted during 3 and 4 December 1980 and 23 May to 1 June 1981. CTD
measurements were not taken during the surveys; shallow depths at all stations
required sampling from a small boat, from which the CTD could not be deployed.
Due to shipboard error only one water temperature was taken (Station 8,
December 1980).
A-i
-------
CONTENTS
Section , Page
A.I INTRODUCTION A-l
A. 2 METHODS A-l
A. 2.1 WATER COLUMN MEASUREMENTS -. . A-5
A. 2.2 GEOCHEMISTRY AND GRAIN SIZE ANALYSIS A-6
A.2.3 BIOLOGICAL MEASUREMENTS ...... A-8
A. 2.4 COMPUTER DATA ENTRY AND ANALYSIS A-10
A. 2.5 QUALITY CONTROL PROGRAM A-10
A. 3 RESULTS AND DISCUSSION A-12
A. 3.1 WATER COLUMN CHARACTERISTICS A-12
A.3.2 SEDIMENT CHARACTERISTICS A-18
A.3.3 TISSUE CHEMISTRY A-27
A.3.4 ELUTRIATE TESTS A-29
A. 3.5 MACROFAUNA A-30
A.3.6 EPIFAUNA A-39
A. 3.7 MICROBIOLOGY A-43
A.4 SUMMARY A-43
REFERENCES A-46
ILLUSTRATIONS
Figure Page
A-l Station Locations, IEC Survey of Atchafalaya River ODMDS
(December 1980) A-2
A-2 Station Locations, IEC Survey of Atchafalaya River ODMDS
(May-June 1981) A-3
A-3 Mean Number of Individuals at Each Station at
Atchafalaya River ODMDS and Vicinity (December 1980) A-34
A-4 Mean Number of Individuals at Each Station at
Atchafalaya River ODMDS and Vicinity (May-June 1980) A-35
A-5 Trellis Diagram Showing Similarity Between Trawls at
Atchafalaya River ODMDS and Vicinity A-42
A-iii
-------
CONTENTS (Continued)
TABLES
Number Page
A-l Sampling Requirements for Atchafalaya River ODMDS
and Vicinity A-4
A-2 Laboratories Performing Analysis of Samples Collected
at Atchafalaya River ODMDS and Vicinity A-5
A-3 Water Column Physical and Chemical Parameters at
Atchafalaya River ODMDS and Vicinity A-13
A-4 Concentrations of Dissolved and Particulate Trace Metals
and Dissolved CHCs at Middepth in the Water Column at
Atchafalaya River ODMDS and Vicinity A-16
A-5 Sediment Grain Size Composition at Atchafalaya River ODMDS
and Vicinity A-19
A-6 Concentrations of Trace Metals, TOC, and Oil and Grease,
Cyanides, and Phenols, and Percentages of Fines and Clay
in Sediments at Atchafalaya River ODMDS and Vicinity
(December 1980) . A-20
A-7 Concentrations of Trace Metals, TOC, and Oil and Grease,
Cyanide, and Phenols and Percentages of Fines and Clay
in Sediments at Atchafalaya River ODMDS and Vicinity
(May-June 1981) A-21
A-8 Correlation Matrix for Sediment Parameters at
Atchafalaya River ODMDS and Vicinity A-23
A-9 CMC Concentrations in Sediments at Atchafalaya River ODMDS
and Vicinity A-25
A-10 Summary of Petroleum Hydrocarbon Analyses for Sediments
at Atchafalaya River ODMDS and Vicinity A-26
A-ll Dry Weight Concentrations of Trace Metals and CHCs in Edible
Portions of Organisms Collected in Trawls at
Atchafalaya River ODMDS and Vicinity A-28
A-12 Results of Elutriate Tests from Sediments Inside and Outside
Atchafalaya River ODMDS A-30
A-13 Rank of Dominant Species for Stations at
Atchafalaya River ODMDS and Vicinity (December 1980) A-32
A-14 Rank of Dominant Species for Stations at
Atchafalaya River ODMDS and Vicinity (May-June 1980) A-33
A-iv
-------
CONTENTS (Continued)
Number Page
A-15 Numerical Abundance of Dominant Species at Each Station
at Atchafalaya River ODMDS and Vicinity . . . _ A-36
A-16 Results of Two-Factorial ANOVAs for Density of
Dominant Species Between Surveys and Stations at
Atchafalaya River ODMDS and Vicinity A-38
A-17 Results of One-Way ANOVAs for Density of
Dominant Species Between Surveys and Stations
at Atchafalaya ODMDS and Vicinity A-39
A-18 Results of SNK Tests for Dominant Species Among Stations
at Atchafalaya River ODMDS and Vicinity A-40
A-19 Species of Invertebrates and Fish Collected in Otter Trawls
at Atchafalaya River ODMDS and Vicinity A-41
A-20 Total and Fecal Coliform Counts at Atchafalaya River ODMDS
and Vicinity A-44
A-v
-------
A.I INTRODUCTION
*
Interstate Electronics Corporation (IEC) conducted field surveys at the
Atchafalaya River ODMDS during December 1980 and May-June 1981. Physical,
chemical, biological, and geological oceanographic data were collected to
assess the effects of dredged material disposal on the marine environment, and
to augment historical information for the area. A major consideration of
survey design was to determine whether any adverse effects identified within
the ODMDS were detectable outside site boundaries.
Methods of collection, results, and interpretations of the survey data are
presented in the following sections. Data are briefly compared with
historical information; however, more comprehensive treatment is given in
Chapter 3 of this EIS.
A.2 METHODS
Survey operations were conducted using the Ocean Survey Vessel ANTELOPE,
Because of generally shallow depths, all samples (except trawls) were
collected from a 16-foot Boston Whaler and processed aboard the Antelope.
Loran-C or radar range and bearing positioning were used for navigation,
providing accuracy within 0.25 nmi. (See Appendix B for Loran-C positioning,
or ranges and bearings, for all sampling locations).
Stations 1 to 5 were located inside the ODMDS, and control Stations
6 to 10 were positioned in predominant upcurrent/downcurrent directions
outside the site (Figures A-l and A-2). Station locations were designed to
determine whether transport of dredged material was occurring outside of the
site boundaries. Samples collected, coordinates, and water depths for all
stations are presented in Table A-l.
Microbiological analyses of sediments and tissues, and several chemical and
physical oceanographic measurements were performed aboard the ANTELOPE; all
other detailed chemical, geological, and biological analyses were performed at
shore-based laboratories listed in Table A-2.
A-l
-------
Kilometers
Nautical Miles
29*20'
A WATER COLUMN
BOX CORE - CHEMICAL AND GRAIN SIZE
* BOX CORE - BIOLOGICAL AND GRAIN SIZE
I
TRAWL TRACK
29*10'N
91-30'
91'20'W
Figure A-l. Station Locations,
IEC Survey of Atchafalaya River ODMDS (December 1980)
A-2
-------
CULF OF MEXICO
A WATER COLUMN
BOX CORE - BIOLOGICAL AND GRAIN SIZE
BOX CORE - CHEMICAL AND GRAIN SIZE
TRAWL TRACK
29*30'
91'30-
91'20'W
Figure A-2. Station Locations,
IEC Survey of Atchafalaya River ODMDS (May-June 1981)
A-3
-------
TABLE A-l
SAMPLING REQUIREMENTS FOR ATCHAFALAYA RIVER
ODMDS AND VICINITY (DECEMBER 1980 AND MAY-JUNE 1981)
UATER COLUMN
HATER SAMPLING ROSETTE
GO-FLOW
1 SAMPLE PER
MI WATER STATION
/
GO- FLOW
TEFLON-LINED
I SAMPLE PER
MI WATER STATION
y / y /
SEDIMENT
BOX CORER. 7 DROPS
GEOLOGICAL-CHEMICAL
2 CORES PER STATION
////// a?V / ,
1
CORE
PER
STA
BIOLOGICAL
5 CORES OR
GRABS PER
STATION
/
8IOTA *
DREOGE/TRAWL
EP [FAUNA AND
MACROINFAUNA
TISSUES
2 TRAWLS PER SITE
/ £>/ /
001
002
003
004
005
006
007
008
009
010
oc
QC
0
OA
QC
08
1
DC
OC
SHALL BOATt
SMALL BOAT
SMALL BOAT
SMALL BOAT
SMALL BOAT
SMALL BOAT
SMALL BOAT
SMALL BOAT
SMALL BOAT
SMALL BOAT
STATIONS
NUMBED
LATITUDE
LONGITUDE
DEPTH
NUMBER
LATITUDE
LONGITUDE
DEPTH
1
29°16106"N
91°27'49"V
4m
1
29°16'06"N
91°27'49"W
2m
2
29°17'40"N
91°26'24"il
3m
2
29°17'40"N
91°26'24"V(
3m
3
29°19'13"N
91°25'00"W
2m
3
29°19'13"N
91°25'00"W
3m
4
29°14'30"N
91°29 10"W
3m
4
29°14'30"N
91°29'10"W
4*
S
29°12'54"N
91°30'33"V
Sffl
5
29°12'M"N
91°30'33"W
4m
6
29°16'24"N
91°24'36"W
3m
6
29°16I24"N
91°24'36"W
4m
7
29°19'54"N
91°26'50"V(
4m
7
29°19'54"N
91°26'50"W
3m
8
29°16'54HN
91°29'30"W
3m
8
29°16'54-N
91°29'30"W
4m
9
29°14'24"N
91°3ri4"H
4m
9
29°14'24"N
91C31'14"W
3m
10
29°12'30"N
91°28'24"H
5m
10
29°12'30"N
91°28'24"W
5m
OA F11t*r clian seanater through on* additional column to d*term1n« extraction efficiency (May-June Survey only)
06 Rinsing efficiency for removal of s*a salts from Nucleopore filters, 1n addition to samples collected at each
designated station
QC One quality control sample taken, 1n addition to samples collected at each designated station
00 Handling blanks for trace metals plus sample
(A) Mercury, cackrium, lead, chromium, anenlc, zinc, nickel, copper, and manganese will be analyzed
(B) Composite simple from both box corn at each designated station
(C) Composite sample from all trawls, plus samples of opportunity from geological-chemical box cores. Species
Identified onboard ship before analysis or preservation, and specimens retained for verification
*A11 dredges/trawls conducted using OSV ANTELOPE
t 16-foot Boston Hhaler
A-4
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TABLE A-2
LABORATORIES PERFORMING ANALYSIS OF
SAMPLES COLLECTED AT ATCHAFALAYA RIVER ODMDS AND VICINITY
Biology
Barry A. Vittor and Associates
Mobile, Alabama
La Mer*
San Pedro, California
Chemistry/Geology
ERCO
Cambridge, Massachusetts
TAXON
Salem, Massachusetts
Jacobs Laboratories*
Pasadena, California
* Denotes quality control laboratory
Sampling equipment, procedures, and preservation methods were in accordance
with the "Oceanographic Sampling and Analytical Procedures Manual" (IEC,
1980). A summary of these methods is presented in the following sections.
A.2.1 WATER COLUMN MEASUREMENTS
A.2.1.1 Shipboard Procedures
Middepth water samples were collected in 5 liter or 30 liter Go Flow
bottles for suspended solids, turbidity, dissolved oxygen, salinity, pH,
dissolved and particulate trace metals, and dissolved chlorinated hydrocarbons
(CHC). Water temperature was measured only at Station 8 during the December
survey. Salinity samples were analyzed with a Beckman salinometer. Water
temperature was measured using a bucket thermometer. Turbidity was measured
with a Hach laboratory turbidimeter, and pK with a Beckman pH meter.
Dissolved oxygen was determined using a modified Winkler method (Strickland
and Parsons, 1972). Water samples for total suspended solids and trace metals
(particulate and dissolved) analyses were transferred from Go-Flo bottles to
2-liter pressure filtration bottles, then filtered through Nucleopore filters.
The filtrate was collected for dissolved trace metals analysis in precleaned
bottles acidified with Ultrex nitric acid. Measured water volumes were
pressure-fed directly from Go-Flo bottles through an Amberlite XAD resin
column for extraction of CHCs (Osterroht, 1977). Filters for particulate
A-5
-------
trace metals and suspended solids, and resin columns for CHCs, were processed
in a positive pressure clean hood and frozen prior to analysis.
A.2.1.2 Laboratory Methods
Total suspended solids were determined gravimetrically on an electrobalance
(Meade et al., 1975). Filters containing particulate trace metal (arsenic,
cadmium, chromium, copper, manganese, nickel, lead, and zinc) samples were
leached for 2 hours with IN Ultrex nitric acid; leachates were analyzed by
flame or graphite furnace atomic absorption spectrophotometry (AAS). Mercury
was determined by acid-permanganate digestion (95°C) of particulate matter,
reduction of ionic mercury with hydroxylamine and stannous sulfates, and
analysis by cold-vapor AAS (EPA, 1979).
Dissolved mercury was analyzed by cold-vapor AAS following acid-
permanganate digestion (95°C) and reduction with hydroxylamine and stannous
sulfates (EPA, 1979). Arsenic was determined by a hydride generation
technique under addition of sodium borohydride and sodium hydroxide (Aandreae,
1977; EPA, 1979). Dissolved cadmium, chromium, copper, manganese, nickel,
lead, and zinc were concentrated using a chelation-solvent extraction method
(Sturgeon et al., 1980), and analyzed by graphite furnace AAS.
CHCs were eluted from resin columns with acetonitrile. The eluate was
extracted three times with hexane, evaporated to near dryness, fractionated on
a florisil column, and analyzed by electron-capture gas chromatography
(Osterroht, 1977). The chromatogram was scanned for presence of polychlori-
nated biphenyl (PCS) mixtures (Arochlors 1016, 1221, 1232, 1242, 1248, 1254,
1260, and 1262), and various pesticides and derivatives (aldrin, dieldrin,
endrin, heptachlor, /3-BHC, DDT, ODD, DDE, and heptachlor epoxide).
A.2.2 GEOCHEMISTRY AND GRAIN SIZE ANALYSIS
A.2.2.1 Shipboard Procedures
2
Sediment sampling was performed with a 0.05 m Ponar grab sampler. Seven
50g sediment samples were collected at each station and frozen for grain size
A-6
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analysis. Sediment samples for geochemical analyses (trace metals, oil and
grease, total organic carbon [TOG], cyanide, phenols, petroleum hydrocarbons,
and CHCs) were collected from the surface 2 cm of two cores per station,
stored in acid-cleaned Teflon jars, and frozen.
A.2.2.2 Laboratory Methods
Sediment grain size was determined by washing sediment samples through
2,000 and 62 fm mesh sieves to separate gravel, sand, and silt/clay fractions
(Folk, 1978). Sand/gravel fractions were separated with 1 phi (0) interval
sieves, dried, and weighed. The silt/clay fractions were analyzed using a
pipette method (Rittenhouse, 1933).
Trace metals (arsenic, cadmium, chromium, copper, manganese, nickel, lead,
and zinc) were leached from 5g to lOg of sediments for 2 hours with 25 ml of
IN nitric acid, and analyzed by graphite furnace MS or inductively coupled
plasma emission techniques (ICP). Mercury was leached from 5g to lOg of
sediment at 95°C with aqua regia and potassium permanganate, reduced using
hydroxylamine sulfate and stannous sulfate, and analyzed by cold-vapor AAS
(EPA, 1979).
Oil and grease were extracted from lOOg sediment samples with an
acetone-hexane mixture, dried, and quantified gravimetrically according to the
method of APHA (1975). TOG in sediments was measured with a Perkin-Elmer
Model 240 Elemental Analyzer (Gibbs, 1977). Analyses for total cyanide and
total recoverable phenols were performed according to methods specified by
APHA (1975) and EPA (1979), as modified for sediment samples.
CHCs were soxhlet extracted from sediment samples using a 1:1 acetone-
hexane solvent. The extract was evaporated, cleaned on a florisil column,
fractionated on a silicic acid column, and analyzed by electron-capture gas
chromatography (EPA, 1974). An additional acid cleanup step was required for
analysis of PCBs. Chromatograms were scanned for the same compounds listed
above in Section A.2.1.2. Petroleum hydrocarbons were extracted from
A-7
-------
sediments with an acetone-hexane solvent and analyzed by column and
glass-capillary gas chromatography (Farrington and Tripp, 1975; Boehm, et al.,
1980).
Elutriate analyses were performed in accordance with the specifications of
EPA/CE (1977). Sediments and unfiltered disposal site water were mixed at a
1:4 ratio by mechanical and air agitation for 30 minutes. After a 1-hour
settling period, test water was filtered, acidified with Ultrex hydrochloric
acid, and analyzed for dissolved trace metals (arsenic, cadmium, chromium,
copper, mercury, manganese, nickel, lead, and zinc) using techniques described
above.
A.2.3 BIOLOGICAL MEASUREMENTS (Including Tissue Chemistry and Coliform)
A.2.3.1 Shipboard Procedures
2
Five macrofaunal samples were collected at each station using a 0.05 m
Ponar grab sampler. Samples were washed through a 0.5 mm screen and organisms
were preserved in 10% formalin in seawater prior to analysis.
A total of six 7.6m otter trawls were conducted to collect epifauna for
analysis of tissue concentrations of CHCs, trace metals, and total and fecal
coliforms. In December, single tows were performed inside (T-l) and outside
(T-2) the ODMDS; in May-June three trawls, were taken inside (T-3, T-4, and
T-5), and one outside (T-6), the ODMDS (Figures A-l and A-2). Information
from the catch was also used to further characterize the benthic and nektonic
communities.
Epifauna from the trawls were sorted in stainless steel trays and
enumerated. Tissue was combined from at least three individuals of each of
the commercially important species captured, aseptically homogenized in a
blender, and cultured within 6 hours for total and fecal coliforms using a
modified most probable number (MPN) technique (APHA, 1975; IEC, 1980). Other
specimens were transferred from the trays to acid-rinsed plastic buckets, and
then into clean plastic bags and frozen for trace metal analyses. Additional
A-8
-------
specimens were transferred to stainless steel buckets with stainless steel
forceps, wrapped in aluminum foil, placed in polyethylene bags, and frozen for
CHC analysis.
Total and fecal colifortns were determined in sediments from the two box
core samples taken for sediment geochemistry. Approximately 30g of sediment
from the surface 1 cm of each sample was collected aseptically; analysis was
initiated within 6 hours after collection. Coliforms were determined using
the MPN technique (APHA, 1975; IEC, 1980).
A.2.3.2 Laboratory Methods
Six dominant macrofaunal species were selected for enumeration in all
samples. Selection of species was based on inspection of initial laboratory
data (species- abundance throughout the site), feeding types, and known
association with environmental conditions, particularly substrates. Each of
the six dominant species was enumerated in all five station replicates, and
mean species abundances were calculated for each station. All samples were
transferred to 70% alcohol for storage.
Analysis of cadmium, chromium, copper, manganese, nickel, lead, and zinc
concentrations in tissues followed techniques described by EPA (1977).
Approximately 5 to lOg of homogenized tissue were digested with nitric acid
and hydrogen peroxide while heated. The digests were then evaporated, diluted
to volume with deionized water, and analyzed by flame or flameless AAS.
Determinations of mercury and arsenic levels in tissues required cold
overnight digestion of a 5g sample with hydrogen peroxide and sulfuric acid,
followed by additions of potassium permanganate and potassium persulfate, with
digestion at 50 to 60°C (EPA, 1977). Mercury was analyzed by cold-vapor AAS,
and arsenic by hydride generation or graphite furnace AAS.
Tissue analyses for CHCs required homogenization of 50g of tissue with
sodium sulfate, extraction with hexane, cleanup, fractionation, and analysis
with electron-capture gas chromatography (EPA, 1974).
A-9
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A.2.4 COMPUTER DATA ENTRY AND ANALYSIS
All data were converted to a standard data format for entry into the Ocean
Data Environmental Evaluation Program (ODEEP), a computerized data base
management system developed by IEC. Statistical analyses included calculation
of means, variances, correlations, and analysis of variance. Correlations
were run between parameter values measured within individual sediment samples
(replicates).
A.2.5 QUALITY CONTROL PROGRAM
Accuracy and precision of shipboard and laboratory procedures and data was
assessed using the quality control program described in this section. Key
elements of the program included:
Collection of quality control samples (sample blanks) to identify
sources of contamination resulting from shipboard handling
Laboratory analysis of spiked (prepared samples having a series of
trace metal concentrations) and replicate samples
Determination of the validity of primary laboratory data through
analysis of replicate field and National Bureau of Standards (NBS)
samples by both the primary and quality control laboratories
x
A detailed description of quality control procedures is presented in the
"Oceanographic Sampling and Analytical Procedures Manual" (IEC, 1980). A
summary of these procedures is included in the following sections. A listing
of quality control data is presented in Appendix C.
A.2.5.1 Interlaboratory Quality Control and Calibration (Appendix C-l)
(a) Analysis of Replicate Samples - The following replicate samples were
collected for analysis by both primary and quality control laboratories:
Nucleopore filters for analysis of particulate trace metals; water samples for
A-10
-------
dissolved trace metals; XAB resin columns for dissolved chlorinated
hydrocarbons; sediment samples for analysis of trace metals, cyanide, phenols,
and petroleum and chlorinated hydrocarbons.
Samples for analysis of tissue contaminants (trace metals and chlorinated
hydrocarbons) were blended and split by the primary laboratory; half of the
sample then was shipped to the quality control laboratory for analysis.
In addition, analyses were performed by both laboratories on NBS reference
materials to determine extraction efficiencies for trace metals in sediments
and tissues.
(b) Identification of Biological Specimens - Taxonomic identifications of
approximately 10 specimens of selected species of macroinfauna were verified
by a quality control laboratory.
A.2.5.2 Shipboard Quality Control Procedures (Appendix C-2)
(a) Comparison of Biological Data Collected Using Two Types of Sampling
Gear - Five box core samples and five Ponar grab samples were collected at
Station 6, Mississippi River-Gulf Outlet ODMDS (EPA, in preparation). Mean
numbers of selected taxa were compared using a Mann-Whitney U-test to
determine if there was a significant difference in the number of organisms
captured by the two sampling methods. Samples were collected and analyzed
using standard procedures described in Section A.2.3.
(b) Trace Metal Contamination From Shipboard Handling of Filters - Standard
shipboard laboratory procedures were followed for handling Nucleopore filters
used to collect trace metal samples. These filters were rinsed with ultrapure
water and frozen prior to analysis for trace metals.
(c) Extraction Efficiency of the XAD Resin Column - Clean seawater was
passed through the column and frozen prior to laboratory analysis for
chlorinated hydrocarbons.
A-ll
-------
(d) Rinsing Efficiency for Removal of Salts from Nucleopore Filters -
Filtered seawater was passed through a clean filter, frozen, and analyzed as a
sample blank for total suspended solids and particulate trace metals.
A.2.5.3 Internal Quality Control for Primary Laboratory (Appendix C-3)
Analysis of Replicate Samples - Internal quality control analyses were
performed by the primary laboratory on replicate samples for trace metals and
chlorinated hydrocarbons in seawater, tissues, and sediments; and for total
organic carbon, oil and grease, cyanide and phenols in sediments. In
addition, analyses were performed on NBS reference materials to determine the
extraction efficiency for trace metals in sediments and tissues.
A.3 RESULTS AM) DISCUSSION
A.3.1 WATER COLUMN CHARACTERISTICS
Salinities varied widely over the study area during both the December 1980
(15.0 to 26.6°/oo) and May-June 1981 (4.9 to 35.5°/oo) surveys (Table A-3).
The lowest salinity (4.9 /oo) was observed in May-June at nearshore Station 7;
however, values at the remaining stations were higher than during the December
survey. The Atchafalaya River is the major source of freshwater to the area
(Heaton, 1978; Schubel et al., 1978) and the general offshore increase in
salinity observed during both sampling periods reflected this input. Spatial
and temporal salinity variations similar to those reported here are typical of
coastal Louisiana and appear to be functions of runoff, rainfall, and wind
effects (Heaton, 1978; Schubel et al., 1978; Fotheringham and Weissberg, 1979;
Weissberg et al., 1980a; Turgeon, 1981). Water temperature in the vicinity of
the ODMDS was recorded only once during the surveys. The value of 19.0°C at
Station 8 during December (Table A-3) is within the range reported for autumn
and winter (about 10 to 22°C) by Turgeon (1981). Spring (May-June) water
temperatures are warmer, ranging from approximately 22 to 32°C (Turgeon,
1981). Since salinity and temperature were recorded only at middepths during
the surveys, the data provide no information regarding vertical water column
structure. Fotheringham and Weissberg (1979) have reported, however, that
A-12
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TABLE A-3
WATER COLUMN PHYSICAL AND CHEMICAL
PARAMETERS AT ATCHAFALAYA RIVER ODMDS AND VICINITY
Station
Sample
Depth
(m)
Temperature
(°C)
Salinity
(*/oo)
Total
Suspended
Solids
(mg/liter)
Turbidity
(NTU)
Dissolved
Oxygen
(mg/liter)
Dissolved
Oxygen
(Z Saturation)
pH
December 1980
1
6
7
8
9
4
2
4
3
4
-
-
-
19.0
-
23.197
23.195
15.004
21.734
26.622
102
18.5
9.85
30.4
15.3
55
7
25
250
13
9.49
10.25
9.47
9.68
10.31
-
-
-
121
-
8.4
8.3
8.4
8.3
8.5
May-June 1981
1
6
7
8
9
2
2
3
2
2
-
-
-
-
-
35.532
28.887
4.930
29.638
30.353
23.0
58.7
59.7 .
44.7
26.9
34
28
30
15
14
8.40
6.77
7.84
8.53
8.94
-
-
-
-
-
8.1
8.1
8.2
8.2
8.2
- Not determined because of shipboard error (determination of Z saturation of dissolved
oxygen requires water temperature)
stratification, primarily caused by salinity differences, is most intense in
this area during spring and summer in response to high river discharge and
limited vertical mixing.
Dissolved oxygen concentrations below the surface are generally highest off
Louisiana during winter, when water column stratification is weak or absent
(e.g., Fotheringham and Weissberg, 1979). Consistent with this observation,
middepth dissolved oxygen levels during the December survey ranged from 9.5 to
10.3 mg/liter, whereas May-June values ranged from 6.8 to 8.9 mg/liter (Table
A-3). Concentrations during both surveys were in the high portions of
A-13
-------
seasonal ranges leported for the area (Turgeon, 1981; Fotheringham and
Weissberg, 1979). The data did not reflect the periodic oxygen depletion at
depth, which has been observed in the general area by Fotheringham and
Weissberg (1979).
Waters in the vicinity of the ODMDS are generally turbid because of shallow
depths, sediment resuspension by waves and winds, and inputs of suspended
particulates in runoff from the Atchafalaya River. Background concentrations
of total suspended solids (TSS) have been reported to approach or exceed 100
mg/liter in the area, particularly during storms (Heaton, 1978; Schubel et
al., 1978; Hausknecht, 1980). A wide range of TSS concentrations (10 to 102
mg/liter) were recorded during the December survey when stormy weather was
encountered (Table A-3); the observed maximum at ODMDS Station 1 was likely
the result of sediment resuspension. No inshore/offshore trends were
indicated by the December results. During the May-June survey the range of
TSS levels was smaller (23 to 60 mg/liter), but concentrations were still
fairly high. The May-June TSS results indicated a generally decreasing
offshore trend, probably reflecting inputs from the Atchafalaya River
(Weissberg et al., 1980a). With the exception of the maximum of 250 NTU at
Station 8 in December, turbidity levels were similar for the May-June (7 to 55
NTU) and December (14 to 34 NTU) surveys; no spatial turbidity trends were
apparent, nor did spatial variations for turbidity and TSS values coincide.
This dissimilarity may have resulted from either subsampling errors, or
passage of water parcels with different characteristics during sampling.
Values for pH were slightly higher in December relative to May-June,
(Table A-3) but all values (8.1 to 8.5) fell within the normal range for
seawater (Home, 1969). Since acid formation is known to occur in coastal
marshes (Baas Becking et al., 1960), the lower pH observed during May-June may
reflect terrestrial influence.
In waters off southeastern Louisiana, concentrations of particulate trace
metals within a given volume of water are largely a function of the quantity
of particles present (Heaton, 1978; Schubel et al., 1978; Tillery, 1980). As
A-14
-------
expected, maximum concentrations for most particulate metals (Table A-4) were
measured at ODMDS Station 1 for December, where the TSS level was also
greatest (102 mg/liter). Particulate trace metal values were slightly lower
at control Station 6 during May-June (TSS - 58.7 mg/liter), followed by
roughly equivalent concentrations for Station 1 in May-June and Station 6 in
December (TSS - 23.0 and 18.5 mg/liter, repectively). Overall ranges were
0.20 to 0.62/ig/liter for arsenic, 0.02 to 0.07 /jg/liter for cadmium, 0.27 to
0.82 /u,g/liter for chromium, 0.40 to 1.2 /xg/liter for copper, 0.004 to 0.016
/mg/liter for mercury, 6.6 to 72 /ig/liter for manganese, 0.32 to 0.91 ^ig/liter
for nickel, 0.46 to 1.9 fig/liter for lead, and 2.0 to 4.9 /ig/liter for zinc.
All concentrations were comparable to ambient levels reported for nearshore
waters in the area (Beaton, 1978; Schubel et al., 1978; Tillery, 1980).
Concentrations of most dissolved metals during the surveys were somewhat
greater in May-June relative to December (Table A-4). Dissolved metal
concentrations appeared to be inversely related to TSS and particulate metal
levels; this inverse relationship may be caused by scavenging of metals from
solution onto sediment particles (Krauskopf, 1956; Heaton, 1978). Concen-
tration ranges for dissolved metals over both surveys were 1.0 to 1.2 jig/liter
for arsenic, <0.07 to 0.16 jig/liter for cadmium, <0.11 to 1.0 jug/liter for
chromium, 0.94 to 2.5 jug/liter for copper, <0.033 to 0.073 jug/liter for
mercury, 0.16 to 18 jig/liter for manganese, 0.38 to 2.0 jug/liter for nickel,
0.05 to 3.2 /ug/liter for lead, and 1.4 to 3.2 jug/liter for zinc. Although
concentrations of certain metals (e.g., manganese and lead) varied widely, all
data were comparable to results of previous studies off southeastern Louisiana
(CE, 1978; Heaton, 1978; Fotheringham and Weissberg, 1979; Weissberg et al.,
1980a,b). No consistent differences in dissolved metal levels between ODMDS
Station 1 and control Station 6 were observed.
Concentrations measured during the surveys for total (particulate plus
dissolved) arsenic, cadmium, copper, chromium, and nickel were below their
respective EPA minimum marine water quality criteria (45 FR 79318 et seq .) .
Total mercury levels at control Station 6 (0.075 and 0.089 ^tg/liter) exceeded
the 24-hour average criterion of 0.025 ^ig/liter during both surveys, but were
well below the single measurement criterion of 3.7 jig/liter (45 FR 79318 et
seq.). Total mercury concentrations at ODMDS Station 1 were lower but
A-15
-------
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indeterminate (<0.047 and <0.037 jug/liter). No criteria have been established
for lead or manganese; however, total lead concentrations were below any known
levels of toxicity to marine biota (45 FR 79318 et seq.), and manganese is not
generally considered an element of environmental concern in marine waters.
Concentrations of most dissolved CHCs examined (see Section A.2.1.2) were
below detectable levels at Stations 1 and 6 during both surveys (Table A-4) .
Only dieldrin (0.1 to 4.1 ng/liter), the DDT derivative pp'DDE (24 to 53
ng/liter), and the PCB Arochlor 1254 (0.4 to 0.6 ng/liter) were present in
measurable quantities. Dieldrin and pp'DDE levels were substantially greater
during May-June relative to December; the higher levels may have been derived
from coastal sources (Lauer et al., 1966). For example, concentrations of
both these compounds are relatively high in Mississippi River waters
(Brodtman, 1976). The maximum dieldrin concentration measured during the
May-June survey (4.1 ng/liter) was somewhat greater than reported previously
(CE, 1978) for the area of the ODMDS (<0.5 to 3 ng/liter); however, it was
within Brodtman's (1976) range for Mississippi River water (2 to 10 ng/liter).
The May-June level exceeded the EPA 24-hour marine water quality crite'rion
(45 FR 79318 et seq.) for dieldrin (1.9 ng/liter), but was well below the
single measurement criterion (710 ng/liter). Comparison of the May-June DDE
concentrations (24 and 53 ng/liter) with the EPA 24-hour (1 ng/liter) and
single measurement (130 ng/liter) criteria for DDT and derivatives yielded
similar results. Concentrations of DDTs determined previously in Mississippi
River water (Brodtman, 1976), and in nearshore waters off Louisiana (CE,
1978; Giam et al., 1978), were somewhat lower than those reported here. PCB
concentrations (detected during the December survey only) were well below
minimum EPA criteria (45 FR 79318) and within or below ranges for the region
reported in the literature (CE, 1978; Giam et al., 1978).
None of the water column parameters measured during the surveys indicated
that dredged material disposal has had a measurable effect on water quality in
the area of the ODMDS. The high TSS level at Station 1 during December was a
possible exception; however, waters off southeastern Louisiana are generally
turbid because of shallow depths and riverine influences. Levels of most
parameters appeared to be typical of the study area.
A-17
-------
A. 3.2 SEDIMENT CHARACTERISTICS
A.3.2.1 Physical
Surficial sediments during both surveys were predominantly silts and clays
at all stations, but exhibited some temporal and spatial textural variability
(Table A-5). Results were similar to previous observations within and
adjacent to the ODMDS (CE, 1978). Overall ranges for mean (n 7) percentages
of sand, silt, and clay were 0.1 to 17.1%, 31.7 to 55.1%, and 28.1 to 68.2%,
respectively. Gravel content was minimal at all stations. Clay content
increased somewhat at most stations between the December and May-June surveys,
whereas percentages of sand and silt usually decreased. Generally finer grain
size composition in May-June was probably the combined result of greater
inputs of clays from the Atchafalaya River, and lower wave and current
energies (i.e., less resuspension of fine bottom sediments) during spring
relative to winter (Weissberg et al., 1980a). Sand content was greatest at
Station 3 during both IEC surveys; this station was closest to the Point
Au Per Shell Reef, where increases in sediment sand content occur (CE, 1978).
Since dredged materials released at the ODMDS are similar to natural sediments
in the area (CE, 1978), no conclusions can be reached regarding disposal
effects on sediment physical characteristics. Dredged material disposal did
not occur between the IEC surveys.
A.3.2.2 Chemical
Concentrations of trace metals in surficial sediments generally exhibited
little variation over the survey area (Tables A-6 and A-7). Mean (n * 40)
concentrations (and ranges) over both surveys were 3.0 /ig/g (1.8 to 4.4/ig/g)
for arsenic, 0.15 /Ltg/g (<0.08 to 0.33 /ig/g) for cadmium, 1.9 jug/g (0.8 to
2.9/ig/g) for chromium, 10 ^ig/g (7.5 to 16 ;ug/g) for copper, 0.055 ;ag/g (0.037
to 0.078 jig/g) for mercury, 590 ;ug/g (250 to 950 ;ig/g) for manganese, 5.5 /tg/g
(3.9 to 9.1 ^ig/g) for nickel, 16 jig/g (9.7 to 24 pg/g) for lead, and 25 yug/g
(17 to 45 /Ltg/g) for zinc.
A-18
-------
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Levels of all metals were similar for the two surveys and exhibited no
consistent spatial or temporal trends. During December 1980, concentrations
of most metals were slightly higher at control Station 9, where clay
percentages were greatest. During the May-June 1981 survey, however, most
concentrations were maximal in one replicate from ODMDS Station 3, where clay
percentages were among the lowest; the zinc concentration (45 yOg/g) in this
sample was particularly high. With the exception of this single zinc value,
trace metal concentrations were generally comparable to those previously
reported for sediments off southeastern Louisiana (CE, 1978; Tillery, 1980;
Weissberg et al., 1980a,b). Arsenic concentrations were relatively high in
most samples; CE (1978) reported similar findings for the area.
Most of the trace metals were significantly (p<0.05) correlated with
percentages of clay in the sediments; cadmium and nickel were exceptions
(Table A-8). Different behavior for cadmium relative to other metals has been
previously documented (Gambrell et al., 1977; Heaton, 1978); no such
documentation exists for nickel, however. Substantially weaker correlations
occurred between fines (silt plus clay) and metals (Table A-8). Apparently,
the clay fraction provides some control over trace metal concentrations in
sediments at the study area, a relationship reported previously for this area
(Weissberg et al., 1980a) and elsewhere (Hallberg, 1974). The significant
positive correlations of all metals (except cadmium) with manganese may
indicate that manganese (and probably iron) oxyhydroxides exert an additional
influence through scavenging and co-precipitation (e.g., Morgan and Stumm,
1964; Heaton, 1978). The trace metals were generally positively correlated
with each other, possibly indicating similar sources and/or behavior in this
environment. Intermetal correlations involving chromium, zinc, copper, and
nickel were generally strongest (Table A-8).
Total organic carbon (TOG) concentrations in sediments, determined only for
the December survey, also showed little variability and were generally low
(Table A-6). Values ranged from 0.15 to 8.2 mg/g, with an overall mean of
1.84 mg/g. No spatial patterns were apparent. Previous measurements in the
area have ranged up to approximately 20 mg/g; data from the IEC surveys were
within the lower portions of historical ranges (Hausknecht, 1980; Weissberg
et al., 1980b).
A-22
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A-23
-------
Concentrations of cyanide and phenols were generally below detectable
levels (Tables A-6 and A-7). Cyanide was detected at low levels (<0.7 jug/g)
at a few stations, both inside and outside the ODMDS, during each survey; no
spatial trends were evident. Cyanide levels were also low (<0.5 mg/g) in a
previous study of the ODMDS and vicinity (CE, 1978). Phenols, determined only
in December, were not detected in any of the samples; no historical data were
available for this parameter.
Sedimentary CHC concentrations at Station 1 and 6 (Table A-9) were
generally low, and only detectable for dieldrin, pp'DDE, pp'DDD, and PCBs
(Arochlors 1016 and 125A). PCB (125A), DDE, and DDD were present in
measurable quantities during both December and May-June surveys; concen-
trations ranged from 2.2 to 5.6 ng/g, and were similar between stations and
surveys. Dieldrin (2.2 to 4.7 ng/g) was detected only in December, whereas
PCB (1016) was present only during May-June (26 to 74 ng/g). No explanation
for these temporal differences can be provided from the limited data
available. All CHC concentrations were within ranges reported by CE (1978)
for the area.
Oil and grease concentrations were high (8 and 15 mg/g) in both Station 1
replicates during December 1980; concentrations at the remaining stations
ranged only from 0.4 to 2.2 mg/g over both surveys (Tables A-6 and A-7). The
reason for the elevated levels at Station 1 is unclear. Since this station is
located within the ODMDS, dredged material disposal must be considered a
possible cause. The most recent disposal to occur prior to the surveys,
however, took place during February 1979. Considering the transient nature of
surficial sediments in this area (Hausknecht, 1980), it is unlikely that any
contaminated dredged material deposits would remain intact for nearly 2 years.
This assumption is supported by the reduced oil and grease concentrations
(<0.5 mg/g) present at Station 1 during the May-June 1981 survey. Addi-
tionally, CE (1978) found oil and grease concentrations to be low (<0.1 mg/g)
in adjacent dredging areas. No other oil and grease data concerning the
vicinity of the ODMDS were available for comparison with the survey results.
A-24
-------
TABLE A-9
CHC CONCENTRATIONS IN SEDIMENTS
AT ATCHAFALAYA RIVER ODMDS AND VICINITY
Station
Dieldrin
pp ' DDE
PCB
pp'DDD
PCB
(Arochlor
1016)
(Arochlor
1254)
December 1980
1
6
4.77
2.22
2.21
2.15
2.53
2.23
ND
ND
5.19
5.55
May -June 1981
1
6
ND
ND
3.20
4.51
3.56
4.05
74.1
26.3
22.9
15.2
ND - None detected
Notes: All data are ng/g; data represent single determinations; no
other CHCs were detected (see Section A.2.1.2 for compounds
examined)
Analyses for ODMDS Station 1 and control Station 6 determined that
sedimentary hydrocarbons were derived from petrogenic and biogenic sources
(Table A-10). Chronic petroleum contamination, as evidenced by the presence
of quantities of unresolved high molecular-weight hydrocarbons, was the
dominant source of hydrocarbons in all samples. Terrigenous biogenic
hydrocarbons, represented by n-alkanes with odd-number carbon chains (nC27,
nC29, nC31), were also present in all samples. The sediments contained minor
amounts of components in the nC20 to nC21 range, which are presumed to be
unsaturated compounds from marine algae (Blumer et al., 1970). The December
sample taken from Station 6 contained a pattern of polynuclear aromatic
hydrocarbons (in the f_ chromatogram) normally associated with combusted
fossil fuels .
A-25
-------
TABLE A-10
SUMMARY OF PETROLEUM HYDROCARBON ANALYSES FOR
SEDIMENTS AT ATCHAFALAYA RIVER ODMDS AND VICINITY
Station
Total
Hydrocarbons
((! / )2>
Total
Saturated (f.)
Hydrocarbons
Total
Aromatic and
Olefinic (f«)
Hydrocarbons
(jUg/g)
Hydrocarbon
Source ^
Classification
December 1980
1
(Inside)
6
(Outside)
120
98
55
58
65
40
3, 1, 2
3, 1, 4, 2
May-June 1981
1
(Inside)
6
(Outside)
*
Sources
111
125
71
77
40
48
3, 1, 2
3, 1, 2
1 Terrigenous biogenic materials (mainly plant waxes)
2 - Marine biogenic hydrocarbons (mainly from plankton)
3 » Chronic petroleum pollution (characterized by large unresolved envelopes
on chromatograms)
4 * Pyrogenic sources (polynuclear aromatics from fossil fuel combustion)
Total hydrocarbon concentrations ranged from 98 to 125 /Ag/g, and did not
vary systematically between stations or surveys (Table A-10). Saturated
hydrocarbon levels (55 to 77 /ig/g) were somewhat higher during May-June than
December, whereas aromatic and olefinic hydrocarbon concentrations were
similar during the two surveys (40 to 65 ;ug/g) No obvious differences
existed between sediments from the ODMDS and control areas. Previous
measurements for total hydrocarbons in somewhat coarser sediments further
offshore yielded generally lower levels than those reported here (Boehm and
Fiest, 1980; Weissberg et al., 1980a,b). The higher hydrocarbon concen-
trations in the survey area may be caused by several factors, including:
(1) greater proximity of the IEC survey area to the shipping channel, and
A-26
-------
associated contamination from petroleum-powered vessels, (2) greater inputs of
particles transported by the Atchafalaya River to sediments closer to shore,
(3) finer grain size and greater absorptive capacity of sediments in the
survey area relative to those sampled in the other studies, or (4) dredged
material disposal. The data are insufficient to differentiate between or
determine the relative importance of these influences.
As described above, sediment physical and chemical characteristics were
generally similar within and adjacent to the ODMDS. No effects of dredged
material disposal could be identified; however, a few relatively high
concentrations for sedimentary chemical constituents (zinc, oil and grease)
were measured within the ODMDS. The survey area is influenced by shallow
water depths, frequent resuspension of bottom sediments by winds and waves,
and inputs of large quantities of fine sediments from riverine sources.
Furthermore, dredged materials released at the ODMDS are similar to natural
sediments in the vicinity, and are probably widely distributed by natural
processes after deposition. Considering the transient nature of surficial
sediments in the survey area, it is not possible to differentiate among
possible sources of contamination with the data collected.
A.3.3 TISSUE CHEMISTRY
Concentrations of trace metals and CHCs in organisms collected in trawls in
the vicinity of the ODMDS are presented in Table A-ll. Trace metal (cadmium,
chromium, copper, mercury, manganese, nickel, lead, and zinc) levels in two
species of penaeid shrimp (Xiphopenaeus kroyeri in December and Trachypenaeus
similis in May-June) were low, and within or below previously reported ranges
for these species in the general area of the ODMDS (Tillery, 1980). Of the
trace metals examined, concentrations were highest for zinc (9.4 to 14 /u,g/g)
and copper (5.1 to 8.9 jig/g); a similar situation was indicated by Tillery1 s
(1980) data. Arsenic concentrations ranged from 5.9 to 8.5 ^ig/g; no
historical data were available for comparison. Mercury concentrations (0.007
to 0.015 ^ig/g) were substantially lower than the action level (1.0 /tg/g)
established by the U.S. Food and Drug Administration (FDA, 1981). Trace metal
concentrations were generally comparable for organisms collected inside
A-27
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o o Z
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o
-------
(Trawls T-l, T-3, T-4, and T-5) versus outside (Trawls T-2 and T-6) the ODMDS.
Since different species were collected during the two surveys, temporal
comparisons are not warranted.
CHC levels were determined in shrimp (X^ kroyeri) during the December
survey and in crabs (Callinectes similis) during May-June. Of the compounds
examined (see Section A.2.1.2), only dieldrin, pp'DDE, and PCB (Arochlor 1254)
were detected. Concentrations in shrimp were substantially lower than those
in crabs; however, all values were well below FDA action/tolerance levels for
edible marine organisms (FDA, 1981; 21 CFR Part 109). CHC levels in crabs
were somewhat greater inside, relative to outside the ODMDS; data are
insufficient to define any cause for this difference. Levels were similar for
shrimp collected inside versus outside the ODMDS. No historical data for CHCs
in these species were available for comparison; however, levels were
comparable to those summarized by Atlas (1981) for other Gulf of Mexico marine
organisms.
A.3.4 ELUTRIATE TESTS
Elutriate test results for sediments collected during May-June 1981 are
presented in Table A-12. The test is intended to indicate the potential for
release of dissolved trace metals from sediments when mixed with seawater.
Results were similar for sediments from Stations 1 (inside ODMDS) and 6
(outside ODMDS). Where differences occurred between the two stations,
releases were generally greater from Station 6 sediments. For example,
manganese releases were indicated in all replicates at both stations, but were
a factor of two greater from Station 6 sediments. Zinc release occurred in
one replicate from each station and, again, was substantially greater for
Station 6. For the remaining trace metals, small or no releases were
detected. Arsenic and cadmium were released in comparatively small quantities
in all replicates. Chromium, copper, mercury, nickel, and lead were retained
and/or scavenged from solution by the solid phase.
A-29
-------
TABLE A-12
RESULTS OF THE ELUTRIATE TESTS FOR SEDIMENTS
FROM INSIDE AND OUTSIDE ATCHAFALAYA RIVER ODMDS
Station
1
(Inside)
6
(Outside)
Sample
Rep #1
Rep #2
Rep #3
Rep #1
Rep #2
Rep #3
Concentrations in Test Water
As
4.1
3.8
4.0
3.4
3.0
3-5
Cd
3.0
1.2
2.1
0.55
3.5
0.43
Cr
<0.80
<0.70
<0.57
<0.69
<0.52
<0.54
Cu
<0.80
<0.70
1.0
<0.69
0.93
<0.54
Hg
<0.033
<0.033
<0.033
0.056
0.038
<0.033
Mn
1,500
1,100
1,300
3,700
3,900
4,200
Ni
<0.80
<0.70
0.80
<0.69
0.62
<0.54
Pb
<0.80
<0.70
<0.57
<0.69
<0.52
<0.54
Zn
<2.0
15
<1.4
<1.7
240
<1.4
Pretest Concentrations
1
6
Sea water
Seawater
1.2
1.5
0.15
0.10
<0.51
<0.57
1.7
0.68
<0.033
0.068
25
12
0.71
<0.57
1.1
<0.57
<1.3
4.4
Seawater collected at middepth at indicated station
Notes: Three replicate tests performed on each sediment sample; all concentrations
are fig/liter in dissolved phase; sediment and water collected in May-June 1981
A.3.5 MACROFAUNA
Macrofaunal assemblages near the Atchafalaya River ODMDS have been examined
during benthic investigations of several proposed salt dome brine diffuser
sites (Parker et al., 1980; Weissberg et al., 1980a,b). These studies
characterized nearshore assemblages as typical of estuarine areas.
Communities were dominated by annual species, the majority of which were
polychaete worms (particularly Mediomastus, Aglaophamus, Paraprionospio,
Magelona, and Owenia), small molluscs (Mulinia and Nassarius), and macro-
crustaceans (shrimp and crabs). Most species displayed seasonal population
fluctuations. Recruitment occurred during winter and spring; populations
declined during summer and autumn due to predation and environmental stresses
such as sediment disturbance by storms or anoxic conditions in bottom waters.
A-30
-------
Stations sampled by IEC in the vicinity of the Atchafalaya River ODMDS were
further inshore and shallower than the proposed brine diffuser sites; however,
the same general macrofaunal assemblage was found. During both surveys
polychaetes dominated the macrofauna (Tables A-13 and A-14), particularly
Mediomastus californiensis, Paraprionospio pinnata, and Cossura spp. During
the December survey the Little surf clam Mulinia lateralis was very abundant
at Stations 7, 8, and 9~probably as a result of seasonal recruitment charac-
teristic of this species (Parker et al., 1980). By the following survey in
late spring (May-June), M. lateralis was abundant only at Station 5 (Table
A-14). Other common members of this assemblage were the carnivorous ribbon
worms Cerebratulus cf. lacteus (and other unidentified rhynchocoelans) and the
snail Nassarius acutus.
2
The overall abundance of individuals (individual/m ) generally increased
from December to May-June due to greater densities of polychaetes (Figures A-3
.and A-4). However, several sharp declines occurred between surveys at
Stations 7 and 8 due to reductions in numbers of Mulinia lateralis.
Based on the information presented in Tables A-13 and A-14, six dominant
species were selected for further analyses. Five of those species,
Mediomastus spp., Paraprionospio pinnata, Sigambra tentaculata, Cossura delta,
and Cossura soyeri, are small-bodied (<2 to 3 cm) deposit feeding polychaetes
(Fauchald and Jumars, 1979) characteristic of this area (Parker et al, 1980;
Weissberg et al., 1980a,b). The sixth taxon, Amphinomidae, represent small
(<1 to 2 cm) carnivorious polychaetes of the Linopherus-Paramphinome species
complex. Numerical data for each of these species is presented in Table A-15.
Densities of each species were examined by analysis of variance (ANOVA) on
log (x+1) transformed data. Two kinds of ANOVAs were used: (1) two-factorial
test (two-way) conducted to examine simultaneously overall differences in
density between surveys and stations, (2) single-factorial (one-way) ANOVA
performed on each set of station data for each survey to examine more specific
differences in patterns of spatial density. Following each one-way ANOVA, the
Student-Newman-Keuls (SNK) multiple-range test (Zar, 1974) was used to
A-31
-------
TABLE A-13
RANK OF DOMINANT SPECIES FOR STATIONS
AT ATCHAFALAYA RIVER ODMDS AND VICINITY (DECEMBER 1980)
Species
Nemertina
Cerebratulus cf. lacteus
Rhynchocoela sp. A
Rhynchocoela sp. I
Annel.ida
Cossura delta
Cossura soyeri
Glycinde solitaria
Linopherus-Paramphinome s pp .
Magelona cf. phyllisae
Mediomastus spp.
Parandalia americana
Paraprionospio pinnata
Sigambra tenCaculata
Streblospio benedicti
Mollusca
Mulinia lateralis
Nassarius acutus
Arthropoda
Ogyrides alphaerostris
Station
1
3
1
6
5
4
2
5
2
5
3
6
1
4
2
4
3
5
6
5
1
3
4
6
2
4
4
2
3
5
6
1
7
5
4
5
5
3
1
8
2
7
6
6
5
6
3
2
5
1
4
5
7
3
4
4
2
5
1
3
8
5
2
3
6
4
5
1
9
4
2
3
3
4
5
1
10
4
7
1
3
6
2
5
4
Note: Ranks are arranged in decreasing abundance (i.e., rank of 1
abundant species)
most
A-32
-------
TABLE A-14
RANK OF DOMINANT SPECIES FOR STATIONS
AT ATCHAFALAYA RIVER ODMDS AND VICINITY (MAY-JUNE 1981)
Species
Cnidaria
Edwards ia sp. A
Nemertina
Cerebratulus cf. lacteus
Rhynchocoela sp. A
Annelida
Carazziella hobsonae
Cossura delta
Cossura soyeri
Glycinde solitaria
Linopherus-Paramphinome spp.
Magelona cf . phyllisae
Mediomastus spp
Owenia sp .
Parandalia americana.
Sigambra tentaculata
Streblospio benedicti
Mollusca
Mulinia lateralis
Nassarius acutus
Nuculana concentrica
Phoronida
Phoronis spp.
Station
1
6
4
2
5
1
7
2
8
6
7
4
3
5
2
3
5
6
5
4
1
5
3
4
5
1
6
4
2
7
5
7
6
8
4
3
9
1
5
5
6
3
7
4
6
2
1
8
7
6
2
1
4
5
5
8
6
5
4
1
7
2
8
9
5
4
8
1
9
3
6
2
10
10
3
8
6
7
2
1
9
4
Note: Ranks are arranged in decreasing abundance (i.e., rank of 1
abundant species)
most
A-33
-------
CULF OF MEXICO
91'30'
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29'20'
29'15'N
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3000
2500
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Figure A-3. Mean Number of Individuals at Each Station
Atchafalaya River ODMDS and Vicinity (December 1980)
10
at
A-34
-------
CULF OF MEXICO
29'15'N
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Atchafalaya River ODMDS and Vicinity (May-June 1981)
A-35
-------
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A-36
-------
determine where significant differences in densities occurred among station
means. For example, if a species was most abundant at stations within the
ODMDS, then those stations would form a subgroup significantly different from
those formed by control stations where densities were lower.
Results of the two-way ANOVAs show that only Mediomastus spp. displayed a
significant increase in density between surveys (Table A-16). Abundance of
this polychaete rose from a total of 180 individuals collected during the
December survey, to 1,074 individuals in collected May-June (Table A-15).
Mediomastus, along with another of the dominant species, Paraprionospio have
been shown to reproduce rapidly (Dauer and Simon, 1976; Pearson and Rosenberg,
1976; Dauer, 1980; Parker et al., 1980) and, as described by Gray (1979), are
generally considered opportunistic. Amphinoraidae, Cossura delta, and £.
soyeri also were more abundant in May-June, but not significantly so. Several
of the species (Amphinomidae , Paraprionospio pinnata, and Sigambra
tentaculata) displayed significant interactions between the two treatment
factors (survey date and station location), but the effect of each factor
alone was not significant. As discussed by Simpson et al, (1960), when an
ANOVA results in nonsignificant treatment factors, but the interaction term is
significant, then factors other than those measured were the cause of the
variance displayed in the data.
One-way ANOVAs demonstrate that nearly all dominant species were
significantly different between stations; this result occurred for data from
both surveys (Table A-17). The only exception was.Mediomastus spp., which was
not significantly different in its densities between stations during the
December survey.
SNK tests showed that no discernable patterns in densities were apparent
for most of the species (Table A-18). The exception was Cossura soyeri, where
greater densities were found offshore. Pertinent to this study was the fact
that no ODMDS stations formed unique subgroups; control stations were usually
mixed with ODMDS stations.
A-37
-------
TABLE A-16
RESULTS OF TWO-FACTORIAL ANOVAs FOR DENSITY OF DOMINANT SPECIES
BETWEEN SURVEYS AND STATIONS AT ATCHAFALAYA RIVER ODMDS AND VICINITY
Species
Amphinomidae
Cossura delta
Cossura soyeri
Mediomastus spp.
Paraprionospio
pinnata
Sigambra tenCaculata
'
Source of
Variation
Survey
Station
Interaction
Residual
Survey
Station
Interaction
Re s id ua 1
Survey
Station
Interaction
Residual
Survey
Station
Interaction
Residual
Survey
Station
Interaction
Residual
Survey
Station
Interaction
Residual
Degrees
of
Freedom
1
9
9
80
1
9
9
80
1
9
9
80
1
9
9
80
1
9
9
80
1
9
9
80
Mean
Square
0.112
0.925
0.579
0.093
0.130
0.803
0.115
0.060
0.001
2.735
0.427
0.060
12.430
0.471
0.271
0.167
0.044
1.069
0.818
0.096
0.200
0.214
0.109
0.050
F-Ratio
0.193 NS
1.598 NS
6.238 *
1.130 NS
6.983 *
1.911 NS
6.002 NS
6.405 *
7.099 *
45.867 *
1.738 NS
1.618 NS
0.054 NS
1.307 NS
8.479 *
1.834 NS
J.963 NS
2.169 *
Significant (p <0.05)
NS - Nonsignificant (p >0.05)
Note: Both factors (i.e., survey, station) assumed random, Model II
ANOVA employed when testing (see Zar, 1974, p. 168)
The ODMDS is a shallow area periodically disturbed by storms. The benthic
assemblage is dominated by species that live for about 1 year and undergo
rapid population expansions (Parker et al., 1980). Results of the IEC surveys
showed that most macrofaunal species were patchily distributed throughout the
A-38
-------
TABLE A-17
RESULTS OP ONE-WAY ANOVAs FOR DENSITY OF DOMINANT
SPECIES AMONG STATIONS AT ATCHAFALAYA RIVER ODMDS AND VICINITY
Species
Amphinomidae
Cossura delta
Cossura soyeri
Mediomastus spp.
Paraprionospio
pinnata
Sigambra tentaculata
Source of
Variacion
Stations
Residual
Stations
Residual
Stations
Residual
Stations
Residual
Stations
Residual
Stations
Residual
December 1980
Degree
of
Freedom
9
40
9
40
9
40
9
40
9
40
9
40
Mean
Square
0.757
0.112
0.439
0.064
1.502
0.069
0.280
0.144
1.550
0.110
0.177
0.065
F-Ratio
6.745*
6.882*
21.701*
1.937 NS
14.077*
2.733*
May-June 1981
Degree
of
Freedom
9
40
9
40
9
40
9
40
9
40
9
40
Mean
Square
0.746
0.073
0.479
0.057
1.659
0.511
0.463
0.191
0.336
0.083
0.147
0.036
F-Ratio
10.172*
8.406*
32.497*
2.427*
4.066*
4.078*
* Significant (p 50.05)
NS Nonsignificant (p >0.05)
study area and several, such as Mediomastus spp. and Paraprionospio pinnata,
are considered opportunistic. Because of the ability of the endemic species
to cope with natural disturbances to their sedimentary habitat, any effects on
densities of these organisms which may have been caused by dredged material
disposal could not be discerned.
A.3.6 EPIFAUNA
Appproximately 600 individuals representing 8 invertebrate and 14 fish
species were collected from otter trawls in the vicinity of the Atchafalaya
River ODMDS (Table A-19). Macrocrustaceans (shrimp and crabs) comprised the
bulk of the invertebrate catch; particularly important were the Seabob shrimp
Xiphopenaeus kroyeri in December, and the Broken-necked shrimp Trachypenaeus
similis and the Lesser blue crab Callinectes similis in May-June. More fish
were collected during May-June relative to December; the Atlantic croaker
Micropogon undulatus was most abundant.
A-39
-------
TABLE A-18
RESULTS OF SNK TESTS FOR DOMINANT SPECIES
AMONG STATIONS AT ATCHAFALAYA RIVER ODMDS AND VICINITY
Species
Stations
Amphinomidae
Cossura delta
Cossura soyeri
Mediomastus spp .
Paraprionospio pinnata
Sigambra tentaculata
7
2
2
1
3
7
(F-ratio
7 3
7
3
December
3
7
. 3
1980
2
8
6
nonsignificant
8 9
1
2
8
6
1
>
1
9
6
10
5
no SNK
4
5
4
9
8
test
10
8
9
5
9
done)
5
6
10
1
4
2
4
5
4
10
6
10
Amphinomidae
Cossura delta
Cossura soyeri
Mediomastus spp.
Paraprionospio pinnata
Sigambra tentaculata
4
2
7
2
9
2
8
7
3
8
10
3
May-June
3
10
2
9
8
9
1981
2
3
10
7
6
10
1
9
5
4
2
8
5
8
6
5
7
7
7
6
8
3
3
5
10
5
1
1
4
4
6
4
9
10
1
1
9
1
4
6
5
6
Notes: Stations are arranged in order of increasing magnitude, homogeneous
subsets are underlined; alpha (Qi) = 0.05 = experimentwise error rate
(see Zar, 1974); see Table A-15 for actual mean values of each station
Macroinvertebrates and demersal fish collected by IEC during both surveys
are characteristic of the area. Furthermore, relative numbers of dominant
organisms collected, such as large numbers of sciaenids (drums and croakers),
were similar to results of other studies conducted in the area (Landry and
Armstrong, 1980; Weissberg et al., 1980a,b).
A-40
-------
TABLE A-19
SPECIES OF INVERTEBRATES AND FISH COLLECTED IN
OTTER TRAWLS AT ATCHAFALAYA RIVER ODMDS AND VICINITY
Species
Common Name
December 1980
ODMDS
T-l
CNTL
T-2
May-June 1981
ODMDS
T-3
T-4
CNTL
T-5
T-6
INVERTEBRATES
Molluscs
Lolliguncula brevis
Polinices duplicatus
Arthropoda
Callinectes similis
Penaeus aztecus
Portunus sp. (juvenile)
Squilla empusa
Trachypenaeua similis
Xiphopenaeus kroyeri
Squid
Moon snail
Leaser blue crab
Brown shrimp
Swimming crab
Mantis shrimp
Broken-necked shrimp
Seabob shrimp
3
-
3
-
-
-
-
25
20
6
2
-
2
-
-
155
3
-
10
' -
-
-
7
"
2
-
36
-
-
1
27
.
-
1
12
5
-
-
-
b
2
50
-
-
-
16
FISH
Clupeidae
Harengula pensacolae
Engraulidae
Anchoa mitchilli
Ophidiidae
Ophidion welshi
Syngnathidae
Syngnathus louisianae
Sciaenidae
Cynoscion arenarius
Larimus fasciatus
Micropogon undulatus
Ephippidae
Chaetodipterus taber
Uranoscopidae
Kathetostoma albigutta
Trichiuridae
Trichiurus lepturus
Stromateidae
Peprilus burti
Triglidae
Prionotus rubio
Cynoglossidae
Sytnphurus plagiusa
Tetradontidae
Lagocephalus laevigatus
Scaled sardine
Bay anchovy
Crested cusk-eel
Chain pipefish
Sand seatrout
Banded drum
Atlantic croaker
Atlantic spadefish
Lancer stsrgazer
Atlantic cutlassfish
Gulf buttterfish
Blackfin searobin
Blackcheek tongue fish
Smooth puffer
Number of Species
Number of Individuals
-
12
-
-
1
-
-
-
1
6
1
-
-
-
8
52
-
-
-
1
6
6
-
1
1
2
-
-
it
-
12
206
7
2
1
-
-
-
18
-
-
3
4
1
3
3
12
62
1
2
1
-
-
-
40
-
-
3
2
-
2
-
10
117
8
4
-
-
-
-
36
-
-
2
3
-
-
-
8
71
4
-
-
-
-
-
25
-
-
3
8
1
1
-
10
116
A-41
-------
Each pair of trawls was compared 'Figure A-5) using Sorensen's quotient of
similarity, QS:
QS = 2J/A + B
where QS is the quotient, A is the number of species in the first trawl, B is
the number of species in the second trawl, and J is the number of species in
common (Southwood, 1966). In December, trawls at ODMDS and control areas were
60% similar in terms of species present. Also, among the May-June trawls,
similarity was usually high (>60%). Conversely, similarity was only 50% or
less between December and May-June trawls. These limited results suggest that
the species composition of epifaunal organisms was temporally variable but
statially homogeneous. QS values are based only on the presence or absence of
species; abundance is not considered. More rigorous quantitative sampling and
analyses would be required to determine if differences in epifaunal
communities exist between ODMDS and control areas.
0
00
O>
r-
u
UJ
Q
?~
CO
9>
r-
LU
Z
D
t
>
<
S
r-
i
H
«N
K
*?
H
^
i
H
irt
i
H
vC
H-
DEC 1980
T-1
\
:§i§i-Svi§
SiSi-S-iS-
T-2
.60
\
MAY-JUNE 1981
T-3
.50
.33
\
SSSSJ Sfififij
B
; '.; X ; 1
T-4
.56
.36
.90
\
M
T-5
.50
.30
.60
.67
\
T-6
.44
.40
.82
.80
.67
\
SIMILARITY - -2L
WHERE A - NUMBER OF SPECIES IN TRAWL A
B - NUMBER OF SPECIES IN TRAWL B
| - NUMBER OF SPECIES IN COMMON
RANGE OF SIMILARITY
.26 to .50
:::;:::::::;: .51 to .75
sssisi 76|oi-°°
Figure A-5. Trellis Diagram Showing Similarity
Between Trawls at Atchafalaya River ODMDS and Vicinity
A-42
-------
A.3.7 MICROBIOLOGY
Low counts of total and fecal coliform bacteria were measured in sediments
during both surveys at the Atchafalaya River ODMDS (Table A-20). In December,
total coliforms ranged from 9 MPN/lOOg at Station 9 to 189 MPN/lOOg at Station
10. Fecal coliforms ranged from nondectable at Stations 3, 8, and 9 to 99
MPN/lOOg at Station 10. During the May-June survey only two stations were
sampled for coliforms in sediments; both yielded very low numbers (Table
A-20).
Crabs and .shrimp collected in trawls contained low numbers of total
coliforms during both surveys. Fecal coliforms were not detected in any of
the tissue samples (Table A-20).
No clear explanation can be given for the presence of coliform bacteria in
the survey area. Although Schwarz et al. (1980) studied bacterial populations
at the nearby Weeks Island brine diffuser site, this study did not include
colifonn bacteria. Possible sources of coliform contamination to the ODMDS
area include sewage residuals transported by the Atchafalaya River, or
disposal of potentially contaminated dredged materials. However, no coliform
analyses have been performed on dredged materials disposed at the ODMDS to
determine if these bacteria are present.
A.4 SUMMARY
Salinities varied widely during both surveys and exhibited an increasing
offshore trend as an apparent response to coastal runoff. Both the minimum
(4.9 /oo) and maximum (35.5 /oo) salinities were measured during the May-June
sampling period. Waters were relatively well-oxygenated during both surveys,
but dissolved oxygen concentrations were slightly lower in May-June relative
to December. Waters in the vicinity of the ODMDS are generally turbid, and
this was reflected in the survey data. Trace metal and CHC levels were
generally comparable to historical data for waters off southeastern Louisiana.
DDE and dieldrin concentrations during May-June, however, exceeded previously
A-43
-------
TABLE A-20
TOTAL AND FECAL COLIFORM COUNTS
AT ATCHAFALAYA RIVER ODMDS AND VICINITY
Station
Sediments
Total
Col i forms
(MPN/lOOg)
Fecal
Col i forms
(MPN/lOOg)
Species
Tissues
Total
Colifonns
(MPN/lOOg)
Fecal
Coliforms
(MPN/lOOg)
December 1980
1
2
3
4
5
6
7
8
9
10
75
181
33
176
40
129
33
10
9
189
24
42
<11
36
10
92
10
<10
<9
99
Callinectes
similis
Callinectes
similis
200
210
<200
<54
May-June 1981
5
10
9
19
<9
<10
Trachypenaeus
similis
114
<29
reported values for the area; these compounds are probably derived from
coastal Louisiana sources. None of the water column parameters reflected any
identifiable effects from dredged material disposal.
Surficial sediments throughout the survey area were predominantly silt and
clay. Concentrations of sedimentary chemical constituents were relatively
uniform, but appeared to be influenced to some degree by sediment grain size,
particularly percentages of clay. Chronic petroleum inputs were determined to
A-44
-------
be the major source of hydrocarbons to sediments both inside and outside the
ODMDS. No effects of dredged material disposal on sediment characteristics
could be identified; however, a few relatively high concentrations for zinc
(one sample) and oil and grease (two samples) were measured within the ODMDS.
It was not possible to differentiate among possible sources of contamination
(e.g., dredged material disposal, riverine inputs) with the data collected
because of (1) the transient nature of surficial sediments in the area, and
(2) the similarity between dredged materials and ambient sediments in the
vicinity of the ODMDS.
The macrofaunal assemblage of the survey area was characteristic of the
general region and dominated by polychaetes. Many of the dominant organisms
were small-bodied, opportunistic species capable of rapid recolonization of
disturbed sediments. Larger macroinvertebrates (mainly shrimps and crabs) and
demersal fish were common throughout the area and probably represented
important predators on populations of infaunal organisms. Any effects of
dredged material disposal on benthic organisms at the ODMDS could not be
identified.
Populations of coliform bacteria were present in the area, but in very low
abundances. Although no explanation can be given for their occurrence,
possible sources of contamination include materials derived from river outflow
or dredged material disposal activities.
A-45
-------
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-------
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A-47
-------
Meade, R.H., P.L. Sachs, F.T. Manheim, J.C. Hathaway, and D.W. Spencer. 1975.
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A-48
-------
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A-49
-------
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Cliffs, NJ. 620 pp.
A-50
-------
Appendix B
LORAN-C COORDINATES AND
RANGE AND BEARING FOR ALL CASTS
B-i
-------
CASTS TAKEN DURING THE IEC SURVEY AT ATCHAFALAYA
(23 MAY THROUGH 1 JUNE 1981)
Station
001
001
001
001
001
001
001
001
001
002
002
002
002
002
002
002
003
003
003
003
003
003
003
004
004
004
Cast
001
002
003
004
005
006
007
008
009
001
002
003
004
005
006
007
001
002
003
004
005
006
007
001
002
003
Type
W
GC
GC
GCE
B
B
B
B
B
GC
GC
B
B
B
B
B
GC
GC
B
B
B
B
B
GC
GC
B
Loran-C
Coordinates
X
-
-
_
_
_
-
_
-
-
_
_
_
-
-
-
-
_
-
-
_
-
_
_
-
Y
-
-
_
_
_
_
.
-
-
.
_
_
-
-
_
-
_
-
_
-
Range
(nrai)
4.78
4.78
4.78
4.78
4.78
4.78
4.78
4.78
4.78
5.71
5.71
5.71
5.71
5.71
5.71
5.71
6.59
6.59
6.59
6.59
6.59 .
6.59
6.59
1.68
1.68
1.68
Bearing
(°True)
231*
231*
231f
231*
231*
231*
231*
231*
231*
227*
227*
227*
227f
227*
227f
227*
222*
222*
222*
222*
222*
222*
222*
262*
262T
262*
B-l
-------
Station
004
004
004
004
005
005
005
005
005
005
005
005
005
005
006
006
006
006
006
006
006
006
006
Cast
004
005
006
007
001
002
003
x 004
. 005
006
007
008
009
010
001
002
003
004
005
006
007
008
009
Type
B
B
B
B
GC
GC
B
B
B
B
B
TRWL
TRWL
TRWL
W
GC
GC
GCE
B
B
B
B
B
Loran-C
Coordinates
X
-
-
-
27609.2
27609.2
27609.2
27609.2
27609.2
27609.2
27609.2
27606.4
(course
015°T)
27614.3
(course
220°T)
27,615.0
(course
225°T)
_
-
_
_
-
-
-
Y
-
-
-
46879.8
46879.8
46879.8
46879.8
46879.8
46879.8
46879.8
46880.4
(course
015°T)
46880.9
(course
220°T)
46881.4
(course
225 °T)
-
_
-
-
-
Range
(nmi)
1.68
1.68
1.68
1.68
-
-
-
-
-
-
-
-
6.35
6.35
6.35
6.35
6.35
6.35
6.35
6.35
6.35
Bearing
(°True)
262*
262f
26 2 f
262f
-
-
-
-
-
-
-
-
-
248 *
24 8 f
248 T
248f
248*
248T
248 f
248f
248 T
B-2
-------
Station
007
007
007
007
007
007
007
007
008
008
008
008
008
008
008
008
009
009
009
009
009
009
009
009
010
010
010
010
Cast
001
002
003
004
005
006
007
008
001
002
003
004
005
006
007
008
001
002
003
004
005
006
007
008
001
002
003
004
Type
W
GC
GC
B
B
B
B
B ,
W
GC
GC
B
B
B
B
B
W
GC
GC
B
B
B
B
B
GC
GC
B
B
Loran-C
Coordinates
X
.
-
_
. -
-
-
-
-
^
-
_
_
_
_
-
-
-
_
-
-
-
_
-
27632.8
27632.8
27632.8
27632.8
Y
_
_
-
_
-
_
-
.
_
_
_
_
_
-
-
_
-
-
-
_
-
46878.1
46878.1
46878.1
46878.1
Range
(nmi)
7.11
7.11
7.11
7.11
7.11
7.11
7.11
7.11
3.19
3.19
3.19
3.19
3.19
3.19
3.19
3.19
0.33
0.33
0.33
0.33
0.33
0.33
0.33
0.33
_
-
-
-
Bearing
(8True)
285f
285T
285T
285*
285r
285T
285*
285T
212t
212f
212T
212f
212T
212T
212f
212T
154f
154*
154T
154*
154T
154T
154r
154t
-
-
-
-
B-3
-------
Station
010
010
010
010
Cast
005
006
007
008
Type
B
B
B
TRWL
Loran-C
Coordinates
X
27632.8
27632.8
27632.8
27627.0
(course
061°T)
Y
46878.1
46878.1
46878.1
46877.9
(course
061°T)
Range
(nmi)
-
-
-
Bearing
(°True)
-
-
-
Note: Master station 7980
Target is Seabuoy FLG "1N" (NOAA Chart No. 11351)
Cast Types
B « Biological
GC - Geochemical
GCE - Elutriate sediment sample
TRWL - Otter trawl
W * Water column
B-4
-------
CASTS TAKEN DURING THE IEC SURVEY AT ATCHAFALAYA (3 AND /» DECEMBER 1980)
Station
001
001
001
001
001
001
001
001
001
002
002
002
002
002
002
002
003
003
003
003
003
003
003
Cast
001
002
003
004
005
006
007
008
009
001
002
003
004
005
006
007
001
002
003
004
005
006
007
Type
W
GC
GC
GCE
B
B
B
B
B
GC
GC
B
B
B
B
B
GC
GC
B
B
B
B
B
Loran-C
Coordinates
X
^
-
.
-
-
-
-
-
-
-
-
-
-
-
-
.
-
.
_
-
-
Y
1|r
-
-
-
-
-
-
-
-
-
-
-
-
-
-
_
.
_
_
-
Range
(nmi)
3.6
3.6
3.6
3.6
3.6
3.6
3.6
3.6
3.6
6.1
6.1
6.1
6.1
6.1
6.1
6.1
2.3
2.3
2.3
2.3
2.3
2.3
2.3
Bearing
(°True)
229a
229a
229a
229a
229a
229a
229*
229*
229*
222a
222*
222a
222a
222a
222a
222a
235b
235b
235b
235b
235b
235b
235b
B-5
-------
Station
004
004
004
004
004
004
004
005
005
005
005
005
005
005
005
006
006
006
006
006
006
006
006
007
007
007
Cast
001
001
003
004
005
006
007
001
002
003
004
005
006
007
008
001
002
003
004
005
006
007
008
001
002
003
Type
GC
GC
B
B
B
B
B
TRWL
GC
GC
B
B
B
B
B
W
GC
GC
B
B
B
B
B
W
GC
GC
Loran-C
Coordinates
X
-
-
-
-
' -
-
11262.7
(course
127°T)
11264.4
11264.4
11264.4
11264.4
11264.3
11264.4
11264.4
_
-
-
-
-
-
-
-
-
Y
_
-
-
-
-
-
46880.5
(course
127°T)
46879.9
46880.0
46880.0
46889.9
46880.1
46880.0
46880.8
-
-
-
-
-
-
-
.
_
-
Range
(nmi)
1.7
1.7
1.7
1.7
1.7
1.7
1.7
-
-
-
-
-
-
-
5.0
5.0
5.0
5.0
5.0
5.0
5.0
5 0
1.6
1.6
1.6
Bearing
(°True)
236a
236a
236a
236a
236a
236a
236a
-
-
-
-
-
-
-
070C
070°
070°
070°
070C
070C
070C
070C
112d
112d
112d
B-6
-------
Station
007
007
007
007
007
008
008
008
008
008
008
008
008
009
009
009
009
009
009
009
009
010
010
010
010
010
Cast
004
005
006
007
008
001
002
003
004
005
006
007
008
001
002
003
004
005
006
007
008
001
002
003
004
005
Type
B
B
B
B
B
W
GC
GC
B
B
B
B
B
W
GC
GC
B
B
B
B
B
W
GC
GC
B
B
Loran-C
Coordinates
X
-
_
_
-
-
-
-
-
-
-
-
_
-
-
-
-
-
-
-
11273.0
11273.1
11273.1
11273.1
11273.1
Y
.
-
_
_
-
-
-
-
-
-
-
-
K
_
-
-
-
-
-
-
46878.3
46878.3
46878.2
46878.2
46878.2
Range
(nmi)
1.6
1.6
1.6
1.6
1.6
3.4
3.4
3.4
3.4
3.4
3.4
3.4
3.4
0.7
0.7
0.7
0.7
0.7
0.7
0.7
0.7
-
-
-
-
Bearing
("True)
112d
112d
112d
112d
112d
185a
185a
185*
185a
185a
185a
185*
185*
200*
200*
200*
200*
200*
200*
200*
200*
-
-
-
-
B-7
-------
Station
010
010
010
010
010
Cast
006
007
008
009
010
Type
B
B
B
GCE
TRWL
Loran-C
Coordinates
X
11273.1
11273.1
11273.1
11273.1
11269.9
(course
Y
46878.2
46878.2
46878.2
46878.2
46879.3
(course
Range
(nmi)
-
-
-
-
_
Bearing
(°True)
-
-
-
_
Note: Master station 7980
a - Target is Seabuoy FLG "1" (NOAA Chart No. 11351)
b - Target is Seabuoy FLG "15" (NOAA Chart No. 11351)
c - Target is Seabuoy FLG "3" (NOAA Chart No. 11351)
d - Target is Seabuoy FLG "2" (NOAA Chart No. 11351)
Cast Types
B « Biological
GC - Geochemical
GCE - Elutriate sample
TRWL - Otter trawl
W - Water column
B-8
-------
Appendix C
QUALITY CONTROL DATA
PURPOSE
This appendix contains quality control data for the IEC Survey of
Atchafalaya River ODMDS. Quality control procedures are summarized in
Appendix A. The following lists the contents of this appendix.
C-i
-------
CONTENTS
Section Page
C-l INTERLABORATORY QUALITY CONTROL C-l-1
C-2 SHIPBOARD QUALITY CONTROL C-2-1
C-3 INTERNAL QUALITY CONTROL PERFORMED BY
PRIMARY LABORATORY . . . C-3-1
TABLES
Number Page
C-l-1 Sample Data Listing C-l-3
C-l-2 Replicate Analyses Performed by Quality Control
Laboratory C-l-5
C-l-3 Identification of Biological Specimens C-l-11
C-2-1 Total Number of Individuals Collected Using a Box Core
as Compared to a Pbnar.Grab C-2-4
C-2-2 Number of Individuals/ra Collected Using a Box Core
as Compared to a Ponar Grab C-2-5
C-2-3 Procedural Blanks to Determine Trace Metal
Contamination from Handling of Filters C-2-6
C-2-4 Extraction Efficiency of XAD Resin Column C-2-6
C-2-5 Rinsing Efficiency for Salt Removal From Filters . . . ; . C-2-6
ERGO REPRINTS Page
Internal Quality Control Data for New Orleans I Surveys C-3-5
Quality Control for Petroleum Hydrocarbon Analyses C-3-31
Internal Quality Control Data for New Orleans II Surveys C-3-33
C-iii
-------
Section C-l
INTERLABORATORY QUALITY CONTROL
C-l-1
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TABLE C-l-3
IDENTIFICATION OF BIOLOGICAL SPECIMENS
VOUCHER SPECIMENS: I.E.G. NEW ORLEANS SURVEYS
POLYCHAE7A
Vittor S Assoc.
LaMer
Owenia fusiformis
Lumbrineris spp.
7U3HO 009-005 (2)
7UOSW 001-OOU (1)
7UUBA 002-006 (5)
7U5CA 008-005 (1)
7UUBA 002-005 (1)
7U1GO 005-012 (10)
Owenia sp.* (2)
Owenia sp. (1)
Owenia sp. (5)
Owenia sp. (1)
Owenia sp. (1)
Lumbrineris spp. (6)
Drilonereis longa** CO
Glycinde solitaria
Travisia hobsonae
Nereis micromma
7U6AT 005-OOU (U)
7U2CA 003-003 (2)
7UUBA OOU-OOU (1)
7UOSW 006-005 (1)
7U7HO 007-003 (1)
7i»6AT 006-005 (2)
7U1GO 002-006 (9)
7U1GO 002-005 (2)
7UOSW 001-OOU (3)
7U1GO 002-005 (1)
7UOSW 001-OOU (3)
7U3HO OOU-003 (1)
739AT 010-007 (1)
7U2CA 011-OQi* (1)
G. solitaria (U)
G\ solitarTa (2)
ff. solitarTa (1)
G~. solitarTa (1)
G\ solitarTa (1)
5". soiitaria (2)
T. hobsonae
T. hobsonae
M. micromma
FT. micromma'
fT. micromma'
FT. micromma
N*. micromma
IT. micromma
(9)
(7)
(3)
(1)
(3)
(1)
(1)
(1)
Comments:
BAV specimens of Nereis micromma and Travisia hobsonae were compared
to type material of those species deposited at the Allan Hancock Foundation.
*Owenia fusiformis : The BAV material is not 0.fusiformis; it superfi-
cially resembles 0. coTlaris in that a collar is present at the base of the
tentacular crown.Tabsent in £. fusiformis). However, they are not Owenia
collaris for the following reasons:a) the neurosetae are intermediate, with
a suggestion of a shoulder in some b) BAV specimens have slightly deeper
dorso-lateral clefts in the collar c) collar on BAV worms is generally more
oblique than that of 0. collaris d) on BAV specimens the notosetae of seti^er
U almost meet;0.collaris setal bundles are more separated e) different staining
patterns in glandular areas with methyl green. Owenia collaris from Santa
Catalina Island, California, the type locality, were used for comparison.
** Drilonereis longa were mixed with the Lumbrineris. This species
belongs to the family Arabellidae; it has no hooded hooks(as in Lumbrineridae).
Projecting acicular spines are present in posterior region. Body is thread-
like, anterior parapodia small S inconspicuous, posteior parapodia bilabiate.
(distinguishes D.longa from D. magna) See Pettibone,1063 (Polychaetes of
New England) and~Hartman,19US (Marine Annelids of North Carolina).
C-l-11
-------
TABLE C-l-3 (continued)
(cone)
BAV LA HER
Ogyrides alphaerostris 741CO 005-010 (9) Ogyrides alphaerostris (9)
Oxyuroatylis smith! (10) 750GO 007-005 Oxyurostylis smith! (10)
Mulinia lateralis (1) 744BA 002-006 Mulinia lateralis (1)
Mulinia lateralis (9) 744BA 007-004 Mulinia lateralis (9)
C-l-12
-------
TABLE C-l-3 (continued)
BARRY A. VITTOR & ASSOCIATES, INC.
ENVIRONMENTAL RESEARCH & CONSULTING
8100 Cottage Hill Raid Mobil*. Alabinw 38909
Phone (205) 681-7236
February 12, 1982
Dr. Andrew Lissner
Interstate Electronics Corporation
Oceanic Engineering
1001 East Ball Road
P. 0. Box 3117
Anaheim, CA 92803
Dear Andy:
Please find enclosed comments concerning the identification
and QC determination of the two polychaete species, Owjjaia fcilfii"
formis and Lumbrineris spp., which were sent to LaMer. I hope
the comments are satisfactory.
Please call if you need further information.
Sincerely ,
J. Kevin Shaw
JKS/dc
Enc.
Mobile Ai.mamn - Shdeil Louisiana - Ocean Springs Mississippi
01-13
-------
TABLE C-l-3 (continued)
With regards Co Owenia fusiformis vs. Owenia sp.: We believe LaMer is
probably correct. We have suspected for some time that £ fusiformis. which
is widely reported from the Gulf of Mexico (see Perkins and Savage, 1975:52),
is not 2- fusiformis. We have never been really sure because we have not
compared our 0. fusiformis with specimens from other localities. In fact,
to clear up the problem completely one needs to examine type material, because
the collar at the base of the tentacular crown could have been easily over-
looked in delle Chiaje's (1841) original description. At any rate, since there
is a problem, it is probably best to call our specimens Owenia sp. A. We feel
our identifications of this taxon were consistent so the change, if necessary,
is "merely" a paper change.
With regards to Lumbrineria spp: This happened because we had to go back
into the sample to pull 10 specimens of Lumbrineris spp. since we do not main-
tain vouchers for indeterminable taxa. In so doing, we inadvertently included
the 4 specimens of Drilonereis longa. This species was not reported in the
New Orleans survey because it was never one of the dominant taxa. It seems we
goofed bat we believe it does not affect the data in any way.
C-l-14
-------
Section C-2
SHIPBOARD QUALITY CONTROL
C-2-1
-------
C-3-1 COMPARISON OF BIOLOGICAL DATA COLLECTED USING TWO TYPES OF SAMPLING GEAR
Two types of sampling gear were used to collect infaunal samples during
2
surveys of six ocean disposal sites in the New Orleans region. A 0.06 m box
core was used at stations deep enough (greater than 18 ft) to be sampled from
2
the ANTELOPE, while a 0.05 m Ponar grab was used at shallow stations sampled
from the small boat (Boston Whaler). To determine if there was a significant
difference between the number of individuals collected using the two types of
sampling gear, five replicate box core samples and five replicate Ponar grab
samples were collected at Station 6, Mississippi River-Gulf Outlet ODMDS (EPA,
in preparation). This station was selected on the basis of its location in a
control area having a relatively homogeneous environment. Numbers of selected
taxa were compared using a Mann-Whitney tJ test (Tables C-2-1 and C-2-2).
These results indicate that when total numbers of individuals were compared,
there was no significant difference between sampling methods for taxa
exhibiting relatively high abundances (Table C-2-1). However, for one taxon
(Platyschnopidae), which exhibited relatively low abundances, there was a
significant difference between methods. When these data were normalized by
2
conversion to numbers of individuals/in , there was no significant difference
between sampling methods for any of the taxa tested (Table C-2-2). Based on
2
these results all infaunal data were converted to numbers of individuals/m so
that differences attributable to sampling methods would be minimized prior to
statistical analysis.
C-2-3
-------
TABLE C-2-1
TOTAL NUMBER OF INDIVIDUALS COLLECTED USING A BOX CORE,
AS COMPARED TO A PONAR GRAB, AT STATION 6, MISSISSIPPI RIVER-GULF OUTLET ODMDS
Replicate
Total
Individuals
N
R
Polychaetes
N
R
Arthropods
N
R
Mediomastus
spp.
N
R
Platyschnopidae
N
R
Box Core
1
2
3
4
5
2R1
111
115
181
151
89
5
4
1
2
7
19
44
73
124
99
41
6
4
1
2
7
20
51
32
47
39
35
1
7.5
2
.4
6
20.5
16
47
79
69
14
7
4
1
2
8
22
29
19
14
15
13
1
3
7
6
8
25
Ponar Grab
6
7
8
9
10
2R2
U
P
33
99
37
142
85
10
6
9
3
8
36
21
>0.20
17
54
19
84
39
10
5
9
3
8
35
20
0.20
12
32
10
40
37
9
7.5
10
3
5
34.5
19.5
0.10>p>0.05
3
27
10
56
26
10
5
9
3
6
33
18
0.10>p>0.05
4
12
21
18
17
10
9
2
4
5
30
15
*
0.01
R Rank
N " Total number of individuals per replicate
Y05(2),5,5 " "
Source: EPA (in preparation)
C-2-4
-------
2 TABLE C-2-2
NUMBER OF INDIVIDUALS/m COLLECTED USING A BOX CORE AS COMPARED
TO A PONAR GRAB AT STATION 6, MISSISSIPPI RIVER-GULF OUTLET ODMDS
Replicate
Total
Individuals
Polychaetes
An thro pods
Mediomastus
spp.
Platyischnopidae
Box Core
1
2
3
4
5
1,850
1,917
3,017
2,517
1,483
733
1,216
2,067
1,650
683
850
533
783
650
583
267
783
1,317
1,150
233
483
317
233
250
217
Ponar Grab
6
7
8 -
9
10
U
P
660
1,980
740
2,840
1,700
17
>0.20
340
1,080
380
1,680
780
17
>0.20
240
640
200
800
740
16
>0.20
60
540
200
1,120
520
18
>0.20
80
240
420
360
340
14
>0.20
U,
23
Note: W0.05(2),5,5 *""; data converted to m using N/.06 for box core and
N/.05 for Ponar grab
Source: EPA (in preparation)
C-2-5
-------
TABLE C-2-3
PROCEDURAL BLANKS TO DETERMINE
TRACE METAL CONTAMINATION FROM HANDLING OF FILTERS
Survey
739
Station
6
Sample Number
N/A
Parameter
TMPA
Value
*
* Not reported; laboratory error
TABLE C-2-4
EXTRACTION EFFICIENCY OF XAD RESIN COLUMN
Survey
739.
739
Station
1
1
Sample Number
1
1
Parameter
Arochlor 1254
Dieldrin
Value
0.9 ng/liter
0.03 ng/liter
TABLE C-2-5
RINSING EFFICIENCY FOR SALT REMOVAL FROM FILTERS
Survey
739
739
746
746
Station
6
6
6
6
Sample Number
1 (replicate 1)
1 (replicate 2)
1 (replicate 1)
1 (replicate 2)
Parameter
TSSA
TSSA
TSSA
TSSA
Value
0.184 mg
0.131 mg
0.698 mg
0.314 mg
C-2-6
-------
Section C-3
INTERNAL QUALITY CONTROL
PERFORMED BY PRIMARY LABORATORY
C-3-1
-------
C-3-1 DATA SUMMARY
This section contains internal quality control data developed by ERGO for
two separate surveys of six New Orleans sites (EPA, in preparation).
Collectively, these data represent a comprehensive quality control program,
and as such, results are listed for both surveys conducted at Atchafalaya
(AT), Barataria (BA), Calcasieu (CA), Houma (HO), Mississippi River-Gulf
Outlet (GO) and Southwest Pass (SW).
Data presented include:
1. Trace metals (Seawater, Tissue, and Sediment)
(a) Recovery of spikes to analyt.e solutions
(b) Duplicate analyses
(c) Efficiency of chelation/solvent extraction system for removing
and preconcentrating metals from seawater
(d) Analysis of NBS reference materials
Note
Data for arsenic in tissues (TMTB)
from New Orleans I surveys are
inaccurate as determined from low
percent recoveries of NBS
reference material using hydride
generation AAS; use of graphite
furnace AAS yielded excellent
results for New Orleans II surveys.
(e) Comparison of aqua regia (strong acid) and 1 N_ HNOo (weak acid)
leach
(f) Analytical blanks
2. Organohalogens (Seawater, Tissue, Sediment)
(a) Recovery of spikes
(b) Duplicate analyses
C-3-3
-------
3. Total Organic Carbon
(a) Duplicate analyses
(b) Analysis of reference material
4. Oil and Grease
(a) Duplicate analyses
(b) Recovery of spikes
5. Cyanide and Phenol
\
(a) Recovery of spikes (Distilled and sediment digestates)
6. Petroleum Hydrocarbons
(a) Analyses of procedural blanks
(b) Duplicate analyses
Coding for the parameters is listed below:
Code Parameter
CNSA Cyanide; sediment
ELSA Elutriate test
OILA Oil and grease; sediment
PCSA PCB; sediment
PCTB PCB; tissue
PCWA PCB; seawater
TMDA Trace metal; seawater (dissolved)
TMPA Trace metal; seawater (particulate)
TMSA Trace metal; sediment
TMTB Trace metal; tissue
TOGA Total organic carbon; sediment
TSSA Total suspended solids; seawater
C-3-4
-------
INTERNAL QUALITY CONTROL DATA FOR NEW ORLEANS I SURVEYS
3.2 Quality Control Data
3.2.1 Trace Metal Analyses
In this s«ction, quality control analyses performed in
conjunction with trace metal analyses are presented.
Recoveries of spikes to analyte solutions are summarized
in Table 37. Ranges of spike recoveries to sediment samples
were as follows: As, 87-103%; Cd, 92-99%; Cr, 87-92%; Cu,
99-106%; Mn, 101-107%; Ni, 97-104%; Pb, 85-91%; and Zn,
94-98%. Ranges of spike recoveries to seawater dissolved and
particulate samples were as follows: 'As, 97-105%; Cd, 74-83%;
Cr, 84-100%; Cu, 94-96%; Mn, 94-117%; Ni, 94-117%; Pb, 90-109%;
and Zn, 103-105%. Ranges of spike recoveries for tissue
samples were as follows: As, 100-101%; Cd, 87-95%; Cr,
93-94%; Cu, 99-100%; Mn, 100%; Ni, 83-116%; Pb, 76-92%; and
Zn, 101-102%.
Duplicate analyses of seawater, tissue, and sediment
samples are summarized in Table 38. All duplicates showed
excellent agreement except Cu and Zn analyses of seawater
(TMDA) and Cr analysis of tissue (TMTB).
The efficiency of the chelation/solvent extraction system
for removing and preconcentrating metals from seawater is
described in Table 39. The mean recoveries and standard
deviations of metal spikes added to the seawater samples
were: Cd, 46 + 6%; Cr, 50 + 26%; Cu, 79 + 23%; Mn, 68 > 33%;
Ni, 56 > 17%; Pb, 88 + 8%; and Zn, 58 + 54%.
Analyses of two National Bureau of Standards Reference
Materials (SRMs) are shown in Tabl*. 40. Analyses of NBS SRM
1645 (River Sediment) using the 1 N HNO3 leach procedure gave
-67-
C-3-5
-------
the following recoveries of metal from the sediment: As, 36%;
Cd, 67%; Cr, 59%; Cu, 40%; Mn, 45%; Ni; 39%; Pb, 80%; and
Zn, 73%. The total analysis for Hg was well within the stated
error limits for the certified value. Analyses of NBS SRM 1566
(Oyster Tissue) showed excellent agreement with certified
values for Cd, Cu, Hg, Mn, Pb, and Zn. Analyses for As,
Cr, and Ni were less accurate due to under-recovery during
digestion or analytical variability.
Table 41 compares results of the 1 N HNC"3 leach of
12 sediments .(samples collected at Station 001 at each site)
with results obtained using an aqua regia (strong acid)
digestion. These results provide additional documentation on
the extraction efficiency of the 1 N HN03 leach for removing
metals from sedimentary material. Compared to the aqua regia
digestion, the 1 N HNC-3 leach recovered the following amounts
(expressed as mean and standard deviation) of metal from the
sediments: As, 17 + 4%; Cd, 115% (two samples only); Cr,
9 + 3%; Cu, 54 + 16%; Mn, 87 + 29%; Ni, 27 + 5%; Pb, 99 + 19%;
and Zn, 38 + 6%.
Analytical blanks for all metal analyses are shown in
Table 42. Blanks were detectable only for Cd, Bg, Mn, Ni, and
Pb in seawater and As, Cr, Hg, and Ni in tissues. In all
other samples, blanks were undetectable.
-68-
C-3-6
-------
TABLE 37
RECOVERY OP METAL SPIKES FROM ANALYTE SOLUTIONS
Sample
Element Identification
AS 739AT 001-003 TMSA
739AT 006-003 TMSA
740SW 004-002 TMSA
740SW 007-006 TMSA
741GO 003-002 TMSA
741GO 008-002 TMSA
742CA 004-002 TMSA
742CA 008-003 TMSA
743HO 005-003 TMSA
743HO 008-002 TMSA
744BA 003-002 TMSA
744BA 005-002 TMSA
740SW 006-001 TMPA
744BA 006-001 TMPA
741GO 001-001 TMDA
742CA 001-001 TMDA
744BA 002-001 TMOA
741GO 003-008 TMTB
743HO 006-010 TMTB
Cd 739AT 006-002 TMSA
739AT 010-003 TMSA
740SW 002-002 TMSA
740SW 003-002 TMSA
741GO 003-002 TMSA
741GO 006-002 TMSA
742CA 002-002 TMSA
742CA 007-004 TMSA
743BO 004-002 TMSA
743HO 006-002 TMSA
744BA 002-003 TMSA
744BA 007-003 TMSA
740SW 006-001 TMPA
740SW 006-001 TMDA
742CA 006-001 TMDA
740SW 006-012 TMTB
742CA 001-011 TMTB
Concen-
tration
Added
54 ug/l
125 ug/l
65 ug/l
67 ug/l
58 ug/l
36 ug/l
76 ug/l
41 ug/l
47 ug/l
39 ug/l
68 ug/l
39 ug/l
40 ug/l
35 ug/l
1.9 ug/l
2.1 ug/l
1.9 ug/l
8.1 ug/l
7.7 ug/l
5.20 mg/l
5.20 mg/l
5.19 mg/l
5.22 mg/l
5.19 mg/l
5.18 ing/1
5.19 mg/l
5.19 mg/l
5.18 mg/l
5.19 mg/l
5.18 mg/l
5.19 mg/l
3.1 ug/l
4.5 ug/l
5.0 ug/l
3.9 ug/l
3.1 ug/l
Concen-
tration
Recovered
53 ug/l
129 ug/l
58 ug/l
60 ug/l
58 ug/l
31 ug/l
70 ug/l
39 ug/l
48 ug/l
34 ug/l
67' ug/l
39 ug/l
40 ug/l
34 ug/l
2.0 ug/l
2.2 ug/l
1.9 ug/l
8.2 ug/l
7.7 ug/l
4.90 mg/l
4.94 mg/l
4.92 mg/l
5.11 mg/l
4.91 mg/l
4.98 mg/l
4.92 mg/l
5.13 mg/l
5.05, mg/l
4.83 mg/l
4.79 mg/l
4.79 mg/l
2.9 ug/l
3.5 ug/l
3.7 ug/l
3.7 ug/l
2.7 ug/l
Recovery
98
103
89
90
100
86
92
95
102
87
99
100
100
97
105
105
100
-101
100
94
95
95
98
95
96
95
99
97
93
92
93
83
78
74
95
87
-69-
C-3-7
-------
TABLE 37 (Cont.)
Sample
Element Identification
Cr 7 39 AT
7 39 AT
740SW
740SW
741GO
741GO
742CA
742CA
743HO
743HO
744BA
744BA
740SW
740SW
742CA
740SW
742CA
Cu 739AT
7 39 AT
740SW
740SW
741GO
741GO
742CA
742CA
743HO
743HO
744BA
744BA
740SW
740SW
742CA
742CA
743HO
009-003
010-003
003-002
008-003
007-003
009-004
003-002
015-001
005-003
007-002
003-002
007-002
006-001
006-001
006-001
006-012
001-011
006-002
010-003
002-002
003-002
003-002
006-002
002-002
007-004
004-002
006-002
002-003
007-003
006-001
006-001
006-001
001-011
006-010
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMPA
TMDA
TMDA
TMTB
TMTB
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMPA
TMDA
TMDA
TMTB ,
TMTB
Concen-
tration
Added
2.
2.
2.
2.
2.
2.
2.
2.
2.
2.
2.
2.
6.
6.
5,
6.
5.
5.
5.
6.
5.
5.
5.
5.
1.
41
40
39
36
33
34
38
38
32
31
38
33
55
25
25
72
51
03
29
23
45
44
14
82
12
17
73
19
28
43
50
53
58
17
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
rag/1
mg/1
mg/1
mg/1
mg/1
mg/1
ug/i
'ug/l
ug/i
ug/l
ug/i
mg/l
mg/1
mg/1
mg/1
mg/1
rag/1
mg/1
mg/1
rag/1
mg/1
rag/1
rag/1
ug/i
ug/i
ug/l
ug/l
mg/1
Concen-
tration
Recovered
2
2
2
2
2
2
2
2
2
2
2
2
6
6
5
6
5
5
5
6
5
5
5
5
1
.19
.15
.21
.17
.14
.15
.14
.17
.07
.11
.14
.03
55
25
21
67
48
.02
.48
.26
.65
.47
.26
.91
.40
.39
.70
.43
.60
41
48
50
58
.16
mg/1
mg/1
mg/1
mg/1
rag/1
mg/1
rag/1
rag/1
mg/1
rag/1
mg/1
rag/1
ug/l
ug/l
ug/l
ug/l
ug/l
rag/l
rag/1
rag/1
mg/1
mg/1
rag/1
mg/1
rag/1
rag/1
rag/1
mg/1
mg/1
ug/l
ug/l
ug/l
ug/l
rag/1
%
Recovery
91
90
92
92
92
92
90
91
89
91
90
87
100
\
100
8.4
93
94
100
103
101
103
101
102
102
105
104
99
105
106
95
96
94
100
99
-70-
C-3-8
-------
TABLE 37 (Cont.)
Sample
Element Identification
Mn 739AT
739AT
740SW
740SW
741GO
741GO
742CA
742CA
743HO
743HO
744BA
744BA
742CA
740SW
742CA
739AT
Hi 739AT
739AT
740SW
740SW
741GO
741GO
742CA
742CA
743HO
743HO
744BA
744BA
740SW
740SW
742CA
740SW
742CA
006-002
010-003
002-002
003-002
003-002
006-002
002-002
007-004
004-002
006-002
002-003
007-003
001-001
006-001
006-001
010-010
006-002
010-003
002-002
003-002
003-002
006-002
002-002
007-004
004-002
006-002
002-003
007-003
006-001
006-001
006-001
006-012
001-011
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMPA
TMDA
TMOA
TMTB
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMPA
TMDA
TMDA
TMTB
TMTB
Concen-
tration
Added
118
128
72
100
80
65
132
139
63
79
84
87
1.
7
8
.9
.0
.1
.5
.0
.3
.6
.4
.6
.5
.2
.5
58
.6
.1
0.677
5.
5.
5.
5.
5.
5.
5.
5.
5.
5.
5.
5.
60
63
53
78
54
57
42
48
22
43
59
55
40
50
58
46
32
rag/1
mg/1
mg/1
mg/1
mg/1
rag/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
ug/i
ug/i
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
ug/l
ug/1
ug/l
ug/l
ug/l
Concen-
tration
Recovered
122
127
74
105
81
66
142
146
67
82
86
88
1.
8
7
.6
.9
.8
.9
.4
.4
.1
.4
.1
.4
.8
.4
58
.9
.6
0.675
5.
5.
5.
5.
5.
5.
5.
5.
5.
5.
5.
5.
49
44
38
80
39
53
33
53
43
32
44
38
41
47
68
38
37
mg/1
rag/1
mg/1
rag/1
rag/1
mg/1
mg/1
mg/1
rag/1
mg/1
mg/1
mg/1
mg/1
ug/l
ug/l
mg/1
mg/1
mg/1
rag/1
mg/1
mg/1
mg/1
mg/1
mg/1
rag/1
mg/1
rag/1
mg/1
ug/l
ug/l
ug/l
ug/l
ug/l
%
Recovery
103
100
104
105
102
102
107
105
106
104
103
101
100
117
94
100
98
97
97
100
97
99
98
101
104
98
97
97
103
94
117
83
116
-71-
C-3-9
-------
TABLE 37 (Cont.
Sample
Element Identification
Pb 739AT
739 AT
740SW
740SW
741GO
741GO
742CA
742CA
743HO
743HO
744BA
744BA
740SW
740SW
742CA
740SW
742CA
Zn 739AT
739AT
740SW
740SW
741GO
741GO
742CA
742CA
743HO
743HO
744BA
744BA
7406O
740GO
740SW
744BA
009-003
010-003
003-002
008-003
007-003
009-004
003-002
015-001
005-003
007-002
003-002
007-002
006-001
006-001
006-001
006-012
001-011
006-002
010-003
002-002
003-002
003-002
006-002
002-002
007-004
004-002
006-002
002-003
007-003
006-001
006-001
003-008
006-010
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMPA
TMDA
TMDA
TMTB
TMTB
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMPA
TMDA
TMTB
TMTB
3
3
3
3
3
3
3
3
3
2
3
3
8
8
7
8
7
7
7
8
6
7
8
8
0.
0.
0.
0.
Concen-
tration
Added
.81
.60
.48
.21
.01
.08
.74
.60
.06
.90
.75
.07
45
34
31
25
25
.17
.71
.07
.98
.44
.44
.84
.35
.63
.73
.49
.00
282
257
667
329
rag/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
rag/1
ug/l
ug/l
ug/l
ug/l
ug/l
rag/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
ug/l
ug/l
ug/l
ug/l
Concen-
tration
Recovered
3
3
3
2
2
2
3
2
2
2
3
2
7
8
6
8
7
7
7
8
6
7
8
7
0.
0.
0.
0.
.46
.17
.10
.80
.55
.63
.37
.23
.74
.63
.55
.71
47
37
28
23
19
.77
.38
.68
.76
.08
.14
.41
.17
.50
.30
.06
.58
291
270
678
332
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
rag/1
mg/1
mg/1
mg/1
ug/l
ug/l
ug/l
ug/l
ug/l
mg/1
rag/1
mg/1
mg/1
rag/1
mg/1
mg/1
mg/1
rag/1
rag/1
mg/1
mg/1
ug/l
ug/l
ug/l
ug/l
Recovery
91
88
89
87
85
85
90
90
90
91
95
88
104
109
90
92
76
95
96
94
98
95
96
95
98
98
94
95
95
103
105
102
101
-72-
C-3-10
-------
en
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o o o o rt w w w w w ^0 ^* rt ^H ^ ^
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-73-
C-3-11
-------
TABLS 39
EVALDATION OF EXTRACTION EFFICIENCY OP PRECONCZHTRATION METHOD
FOR SEAWATZR ANALYSES OF Cd, Cr, Cu,
Mn, Ni, Pb, and
Zn
Sanpl*
Sl«Mnt Identification
Cd 739AT 001-001 WE*
74100 006-001 TMDA
742CA 001-001 TMDA
7438O 001-001 TMDA
Cr 739AT 001-001 TMDA
741GO 006-001 TMDA
742CA 001-001 TMDA
743BO 001-001 TMDA
Ctt 739AT 001-001 TMDA
74100 006-001 TMDA
742CA 001-001 TMDA
743HO 001-001 TMDA
Ml 739AT 001-001 TMDA
741OO 006-001 THE*
742CA 001-001 TMEA
743BO 001-001 OffiA
HI 739AT 001-001 Q1DA
741GO 006-001 TMDA
742CA 001-001 TMDA
743BO 001-001 TMDA
Pb 739AT 001-001 TMDA
741OO 006-001 TMDA
742CA 001-001 TMDA
743HO 001-001 TMDA
Zn 739AT 001-001 TMDA
74100 006-001 TMDA
742CA 001-001 TMDA
743HO 001-001 TMDA
Cone«ntrat±on
Add*d (^g/1)
0.73
0.89
1.1
1.4
0.45
0.53
1.3
2.3
1.8
2.3
2.5
3.4
1.2
1.3
3.5
4.3
1.3
1.5
5.9
7.8
- 3.3
3.9
3.0
3.6
1.9
2.8
8.4
11
Concentration
ttecovwrad (pg/1)
0.33
0.48
0.45
0.59
0.11
0.-45
0.84
0.98
1.5
1.2
2.6
2.3
1.3
1.0
0.93
2.7
0.94
0.48
3.5
4.5
3.2
3.2
2.4
3.3
2.6
1.4
2.4
1.8
% Racovery*
46 * 6
50 + 26
79 * 23
68 * 33
56 + 17
88 * 8
58 + 54
*M*a& and vtandard daviation.
-74-
C-3-12
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C-3-14
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C-3-21
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-------
3.2.2 Organohalogen Analyses
Table 43 shows recovery of organohalogens from the three
matrices of interest. Aroclor 1221 was spiked as this is the
lightest of the PCB mixtures and recoveries of the other PCBs
should be comparable to or greater than those observed for
Aroclor 1221.
Recoveries of organohalogens from seawater are slightly
lower in some cases than those of Junk et al. (1974) who.
reported recoveries ranging from 47% for Aldrin to 96% for DOT
using XAD-2 resin and aqueous samples. A duplicate spike for
single components showed excellent reproducibility.
Spiked sediment and tissue samples show acceptable
recoveries with the exception of raethoxychlor, and op'DOB,
which were not found in any samples. The tissue spike was
performed on a sample which contained significant amounts of
organohalogens, necessitating a background correction before
calculation of spike recovery. The high recovery for pp'DDT
may h-ave been caused by an artifact compound coeluting the
pp'DDT in the spiked extract. Also, separate filets were
analyzed, rather than a subsample of the homogenate.
Sample duplicate results are shown in Table 44. Sediment
duplication is complicated in the case of dieldrin by inter-
ference in the sample f-2. Due to our lower sensitivity for a
multicomponent mixture of PCBs relative to single component
pesticides such as pp'DDE, the PCSA Aroclor 1254 duplicate is
probably an accurate reflection of reproducibility as the
limits of our sensitivity are approached.
-85-
C-3-23
-------
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C-3-24
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-87-
C-3-25
-------
3.2.3 Total Organic Carbon Analyses
Quality control data associated with total organic
carbon analyses are shown in Table 45. Duplicate analyses
(Table 45a) were in excellent agreement with differences
between replicates generally less than 10%. Analyses of
certified reference materials agreed well with certified
values.
3.2.4 Oil and Grease Analyses \
Quality control data associated with oil and grease anal-
yses are shown in Table 46. Duplicate analyses (Table 46a)
showed reasonable agreement and spike recoveries of SAE 10
crude oil averaged 88% (Table 46b).
3.2.5 Cyanide Analyses
Quality control data associated with cyanide analyses are
shown in Table 47. Recovery of cyanide spikes to sediments
are shown in Table 47a. Recovery of distilled cyanide spikes
(additions of cyanide to blank solutions which are processed
in a manner identical to sediment samples) are shown in
Table 47b. In all but three cases, recoveries were greater
than 80%.
3.2.6 Phenol Analyses
Quality control data associated with phenol analyses are
shown in Table 48. Recoveries of phenol spikes to sediment
samples ranged from 74-96% (Table 48a). Recoveries of dis-
tilled spikes ranged from 93-130%.
-88-
C-3-26
-------
TABLS 45*
RESULTS OF DUPLICATE ANALYSES FOR TOTAL ORGANIC CARBON
Sample Identification TOC (mg/g)
739AT 010-002 TOCA 0.63, 0.58
744BA 002-002 TOCA 3.8, 3.6
744BA 003-001 TOCA 8.2, 7.9
739AT 001-002 TOCA 8.2, 7.9
74100 006-003 TOCA 2.0, 2.0
739AT 004-002 TOCA 1.1, 1.2
739AT 004-002 TOCA 4.1, 3.9
740SW 008-002 TOCA 2.8, 2.5
742CA 004-001 TOCA 4.2, 4.5
TABLE 45b
RESULTS OF ANALYSES OF BETEREtlCE MATERIAL FOR TOTAL ORGANIC CARSON
Sample Identification TOC (mg/g)
LKO-1
- certified value 8.79 + 0.08
- iMAflurvd value 9.03
UDCO-2
- certified value 0.51 + 0.02
- oeaaured value 0.48
-89-
C-3-27
-------
TABLE 46a
RESULTS OF DUPLICATE ANALYSES FOR OIL AMD GREASE
Sample Identification Oil and greaee (019/9)
739AT 010-003 OILA 0.67, 0.98
740SW 010-002 OILA 0.13, 0.22
742CA 009-003 OILA 0.11, 0.16
742CA 012-002 QUA 0.49, O.SO
742CA 014-002 OILA ' 0.22, 0.20
743HO 009-002 OILA 0.01, 0.01
TABU 46b
RECOVER? OF SPIKES WITH SAB 10 LUBE OIL
Concentration Concentration
Added Recovered % Recovery
Spike 1 1.67 1.29 77
Spike 2 0.85 . 0.83 98
-90-
C-3-28
-------
TABLE 47*
RECOVERIES OF CYANIDE SPIKES FROM SEDIMENT DIGZSTATB3
Sample Identification
739AT 001-003 CNSA
739AT 009-003 CNSA
740SW 009-002 CNSA
74100 003-002 CNSA
741GO 010-002 CNSA
742CA 001-003 CNSA
742CA 011-002 CNSA
742CA 015-001 CNSA
742CA 004-001 CNSA
\
Cyanide Cyanide
Added (pg) Recovered (per)
50
SO
50
50
50
SO
50
50
SO
27
23
30.5
41.5
46.5
45.5
45
40
45
% Recovery
54
46
61
83
93
91
90
80
90
76 * 18
TABLZ 47b
RECOVERIES OF
CYANIPE SPIKES*
Spike Number
1
2
3
4
5
' 6
7
8
9
10
Cyanide
Added (ug)
50
SO
so
so
50
50
SO
SO
50
50
Cyanide
Recovered (jig)
46
42.5
47
46
49.5
46.5
45
43
45.5
40.5
% Recovery
92
95
94
92
99
93
90
86
91
81
Distilled spikea are additions o£ cyanide to the blank solution
which are then distilled and analyzed as samples. These recoveries serve
as a check on the accuracy of the method. One distilled spike was ana-
lyzed for each batch of samples.
-91-
C-3-29
-------
TAflLB 48*
RECOVERIES OF PHENOL SPIKES FROM SEDIMENT DIGE5TATE5
Sample Identification
739AT 006-003 OLSA
740SW 001-003 OLSA
740SW 006-002 OLSA
74100 006-002 OLSA
741GO 007-003 OLSA
742CA 006-002 OLSA
742CA 013-002 OLSA
743BO 001-002 OLSA
743HO 010-002 OLSA
Phenol
Added (ug)
200
200
200
200
200
200
200
200
200
Phenol
Recovered (ug)
158
148
164
154
189
177
173
192
176
% Recovery
79
74
82
77
95
89
91
96
88
TMLX 48b
RECOVERIES 07 DISTILLED PHENOL SPIKES*
SpiJce number
1
2
3
4
S
6
7
a
9
10
u
12
13
14
Phenol
Added (ug>
200
200
200
200
200
200
200
200
200
200
200
200
200
200
Phenol
Recovered (ug)
194
260
201
396
201
198
197
201
191
190
205
205
212
185
% Recovery
97
130
101
99
101
99
99
101
96
95
103
103
106
93
Distilled spikes are additions of phenol to the blank solution
which are then distilled and analyzed as samples. Ibese recoveries serve
as a check on the accuracy of the method.
-92-
C-3-30
-------
QUALITY CONTROL FOR PETROLEUM HYDROCARBON ANALYSES
3. Quality Assurance Data
One procedural blank and one replicate sample were
analyzed in support of the 14 sediment samples. The proce-
dural blank contained negligible amounts of total lipids (2
ug/g), total f2 (1 ug/g), resolved fi (0.00 ug/g), total
ti (1 ug/g) and resolved f2 (0.03 ug/g). The reported
values were not corrected for concentrations of hydrocarbons
in the blank. No peaks in the blank chromatogram interfered
with the quantitation of any individual components.
One sediment sample, 744-BA-001-001 was split into two
replicate aliquots which were analyzed individually. The
results of the duplicate analyses are shown in Table 2. The
gravimetric concentrations agree to wihin 10 to 20 percent.
However, the gas -chromatographic concentrations agree to
within 20 to 100 percent. This sample contained some of the
lowest concentrations of hydrocarbons wnich might explain
some of the discrepancy.
-7-
C-3-31
-------
TABLE 2
QUALITY ASSURANCE DATA FOR PETROLEUM HYDROCARBON ANALYSIS
SAMPLE 744-BA-001-001
PARAMETER
Total Lip id s (ug/g)
Total £]_ Grav (ug/g)
Resolved fj, GC (ug/g)
CPI
ALK/ISO
Total £2 Grav (ug/g)
Resolved £2 GC (ug/g)
Source Classification -
nC15
nC16
nC17
Pristane
nC26
nC27
nC28
nC29
REPLICATE 1
140
12
0.34
6
-
13
0.66
3,1
0.002
0.003
0.008
0.007
0.009
0.038
0.008
0.052
REPLICATE 2
131
16
0.63
3.5
-
16
0.74
3,1
0.004
0.003
0.009
0.011
0.017
0.064
0.022
0.105
-8-
C-3-32
-------
INTERNAL QUALITY CONTROL DATA FOR NEW ORLEANS II SURVEYS
3.2 Quality Control Data
3.2.1 Trace Metal Analyses
In this section, quality control analyses performed in
conjunction with trace metal analyses are presented.
Recoveries of spikes to analyte solutions are summarized
in Table 43. Ranges of spike recoveries to sediment samples
were as follows: As, 98-137%; Cd, 92-97%; Cr, 82-88%;
Cu, 97-102%; Hg, 83-132%; Mn, 102-107%; Ni, 89-98%; Pb,
88-94%; and Zn, 94-99%. Ranges of spike recoveries to
seawater dissolved and particulate samples were as follows:
As, 105-108%; Cd, 77-99%; Cr, 94-103%; Cu, 100-110%; Hg,
100%; Mn, 83-103%; Hi, 97-103%; Pb, 102-108%; and Zn,
100-106%. Ranges of spike recoveries for tissue samples
were as follows: As, 80-95%; Cd, 100%; Cr, 90-105%; Cu,
104-105%; Mn, 106-107%; Ni, 103-104%; Pb, 100-104%; and Zn,
101-103%. Ranges of spike recoveries for elutriate samples
were as follows: As - 86-100%; Cd, 86-106%; Cr, 71-95%; Cu,
86-113%; Hg, 88-108%; Mn, 98-106%; Ni, 81-103%; Pb,42-126%;
and Zn, 98-113%.
Duplicate analyses of seawater, tissue, and sediment
samples are summarized in Table 44. All duplicates showed
.excellent agreement.
The efficiency of the chelation/solvent extraction system
for removing and preconcentrating metals from seawater is
described in Table 45. The mean recoveries and standard
deviations of metal spikes added to the seawater samples were:
Cd, 111 + 50%; Cr, 33 + 15%; Cu, 87 ± 24%; Mn, 107 + 55%;
Ni, 99 + 25%; Pb, 98 + 37%; and Zn, 46 + 24%.
-79-
C-3-33
-------
TABLE 43
RECOVERY OF METAL SPIKES FROM ANALYTE SOLUTIONS
Ele- Sample
ment Identification
As 745CA
745CA
746AT
746AT
747HO
747HO
748BA
74 88 A
749SW
749SW
'750GO
750GO
74SCA
74SCA
746AT
747HO
748BA
749SW
749SW
750GO
750GO
745CA
749SW
746AT
750GP
745CA
750GO
006-002
010-003
004-002
008-003
002-001
009-001
001-001
006-002
004-001
010-001
005-002
007-003
001-004
006-004
001-004
001-004
006-004
006-004
001-004
006-004
001-004
001-010
003-009
006-001
006-001
006-001
006-001
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
ELS A
ELS A
ELS A
ELS A
ELS A
ELS A
ELS A
ELSA
ELS A
TMTB
TMTB
TMPA
TMPA
TMOA
TMDA
Concen-
tration
Added
73
69
83
82
60
64
61
70
100
76
82
Rep
Rep
Rep
Rep
Rep
Rep
2
3
2
1
2
3
Seawatec
Blank
Sea water
6
4
6
3
9
5
3
4
3
3
4
87
.3
.5
.3
.7
.8
.7
.6
.0
.5
62
82
51
32
.7
.4
ug/i
ug/i
ug/i
ug/i
ug/l
ug/i
ug/l
ug/l
ug/i
ug/l
ug/i
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
Concen-
tration %
Recovered Recovery
80
74
85
87
69
74
60
96
121
83
92
5
4
5
3
8
5
3
3
3
4
4
96
.9
.3
.8
.7
.6
.0
.8
.6
.0
59
66
54
34
.0
.6
ug/i
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l '
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l .
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
110
107
102
106
115
116
98
137
121
109
112
110
94
96
92
100
88
88
106
90
86
95
80
106
106
108
105
-80-
C-3-34
-------
TABLE 43 (Cont.)
Ele- Sample
nent Identification
Cd 745CA
74 6 AT
747HO
748BA
749SW
750GO
745CA
745CA
747HO
748BA
748BA
749SW
749SW
740GO
746AT
750GO
745CA
749SW
745CA
746AT
010-002
008-002
006-002
002-002
003-001
010-002
001-004
006-004
001-004
002-004
006-004
006-004
001-004
006-004
006-001
006-001
006-001
006-001
001-010
005-009
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
ELS A
ELS A
ELS A
ELSA
ELSA
ELSA
ELSA
ELSA
TMPA
TMPA
TMOA
TMDA
TMTB
TMTB
Rep 2
Rep 3
Rep 2
Rep 3
Rep 1
Rep 2
Sep 3
Rep 3
Concen-
tration
Added
2.
2.
2.
2.
2.
2.
7
8
9
8.
8
56
59
56
57
57
57
.3
.2
.8
65
.1
575
578
697
3
3
15
6
3
.6
.3
.1
.7
.5
3.6
mg/1
»g/i
rag/1
rag/1
rag/1
rag/1
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
Concen-
tration t
Recovered Recovery
2.
2.
2.
2.
2.
2.
7
7
10
8
8
41
38
41
50
50
45
.1
.3
.2
.2
.8
510
603
711
3
3
11
6
3
3
.0
.1
.6
.6
.5
.6
rag/1
mg/1
rag/1
rag/1
mg/1
rag/1
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
94
92
94
97
97
95
97
89
104
95
109
106
104
102
83
94
77
99
100
100
-81-
C-3-35
-------
TABLE 43 (Co.nt.)
Ele- Sample
ment Identification
Cr 745CA
746AT
747HO
748BA
749SW
750GO
745CA
74SCA
746AT
746AT
747HO
748BA
749SW
749SW
746AT
750GO
745CA
749SW
745CA
746AT
749SW
010-002
008-002
006-002
002-002
003-001
010-002
001-004
006-004
001-004
006-004
001-004
002-004
001-004
006-004
006-001
006-001
006-001
006-001
001-010
005-009
003-009
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
ELS A
ELS A
ELS A
ELS A
ELS A
ELSA
ELSA
ELSA
TMPA
TMPA
TMDA
TMOA
TMTB
TMTB
TMTB
Rep 2
Rep 3
Rep 1
Rep 2
Rep 2
Rep 3
Sep 1
Rep 3
Concen-
tration
Added
2.65
2.76
2.16
2.28
2.45
2.21
50
50
50
50
50
50
50
55
54
30
31
31
34
38
39
rag/1
mg/1
mg/1
og/i
mg/1
»g/i
ug/l
ug/i
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
Concen-
tration
Recovered
2.23
2.30
2.61
2.58
2.77
2.57
39
42
36
44
47
43
47
50
51
27
32
29
34
34
41
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
%
Recovery
84
83
82
88
88
86
79
84
71
89
95
85
94
. 91
94
90
103
94
91
90
105
-82-
C-3-36
-------
TABLE 43 (Cont.)
Ele- Sample
ment Identification
Cu 745CA
746AT
747HO
748BA
749SW
750GO
74SCA
74SCA
746AT
746AT
747HO
' 748BA
748BA
750GO
746AT
750GO
745CA
749SW
745CA
749SW
010-002
008-002
006-002
002-002
003-001
010-002
001-004
006-004
001-004
006-004
001-004
002-004
006-004
001-004
006-001
006-001
006-001
006-001
001-010
003-009
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
ELS A
ELSA
ELS A
ELSA
ELSA
ELSA
ELSA
ELSA
TMPA
TMPA
TMOA
TMOA
TMTB
TMTB
Rep 2
Rep 3
Rep 1
Rep 2
Rep 2
Rep 3
Rep 1
Rep 1
Concen-
tration
Added
2.85
3.87
3.19
2.93
3.52
2.63
67
50
50
59
57
50
61
69
101
36
69
56
1.67
2.33
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
ug/i
ug/1
ug/1
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
mg/1
mg/1
Concen-
tration
Recovered
2.77
3.82
3.18
2.87
3.58
2.54
69
55
46
61
48
57
64
74
94
36
76
56
1.75
2.43
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
mg/1
mg/1
%
Recovery
97
99
100
98
102
97
104
110
91
102
86 '
113
104
108
93
100
110
100
105
104
-83-
C-3-37
-------
TABLE 43 (Cont.)
Ele- Sample
raent Identification
Concen- Concen-
tration tration %
Added Recovered Recovery
Hg 745CA 008-003 TNSA
746AT 007-002 TMSA
749SW 009-003 TMSA
7SOGO 010-002 TMSA
747HO 006-004 ELSA Rep 3
748BA 006-004 ELSA Rep 1
749SW 001-004 ELSA Rep 1
749SW 006-004 ELSA Rep 3
746AT 001-001 TMOA
0.018 ug
0.019 ug
0.018 ug
0.100 ug
o.oso ug
0.050 ug
0.025 ug
0.050 ug
0.022 ug
0.025 ug
0.021 ug
0.0083 ug
0.045 ug
0.054 ug
0.022 ug
0.052 ug
o.oso ug 0.05,0 ug
122
132
115
83
90
108
88
104
100
-84-
C-3-38
-------
TABLE 43 (Cont.)
Ele- Sample
ment Identification
Mn 745CA
746AT
747HO
748BA
749SW
750GO
745CA
746AT
747HO
748BA
749SW
749SW
746AT
750GO
746AT
750GO
745CA
749SW
010-002
008-002
006-002
002-002
003-001
010-002
001-004
001-004
006-004
002-004
006-004
001-004
006-001
001-001
006-001
006-001
001-010
003-009
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
ELSA Rep 1
ELSA Rep 1
ELSA Rep 3
ELSA Rep 2
ELSA Rep 2
.ELSA Rep 1
TMPA
TMPA
TMOA
TMOA
TMTB
TMTB
Concen-
tration
Added
26
81
45
37
57
12
3
3
3
4
3
3
.38
.47
.85
.49
.11
.24
.34
.26
.95
.03
.51
.50
582
27
310
29
161
417
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
Concen-
tration %
Recovered Recovery
27
83
47
38
60
12
3
3
4
4
3
3
.03
.83
.54
.81
.87
.53
.27
.42
.20
.22
.43
.47
601
28
320
24
173
444
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
ug/l
ug/l
ug/l
ug/i
ug/l
ug/l
102
103
104
104
107
102
98
105
106
105
98
99
103
104
103
83
107
106
-85-
C-3-39
-------
TABLE 43 (Cont.)
Ele- Sample
ment Identification
Ni 745CA
746AT
747HO
748BA
749SW
750GO
745CA
745CA
746AT
746AT
747HO
748BA
748BA
749SW
749SW
750GO
. 746AT
750GO
745CA
749SW
745CA
749SW
010-002
008-002
006-002
002-002
003-001
010-002
001-004
006-004
001-004
006-004
001-004
002-004
006-004
001-004
006-004
001-004
006-001
006-001
006-001
006-001
001-010
003-009
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
ELS A
ELS A
ELS A
ELS A
ELS A
ELS A
ELS A
ELSA
ELS A
ELSA
TMPA
TMPA
TMOA
TMDA
TMTB
TMTB
Rep
Rep
Rep
Rep
Rep
Rep
Rep
Rep
Rep
Rep
2
3
1
2
2
3
1
1
3
1
Concen-
tration
Added
2.82
3.29
2.89
2.86
3.08
2.90
68
50
50
56
50
56
58
68
61
67
68
25
59
58
59
91
mg/1
mg/1
mg/1
mg/1
mg/1
mg/1
ug/l
ug/1
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
Concen-
tration
Recovered
2.69
3.07
2.70
2.80
2.99
2.72
60
49
48
45
51
55
57
63
63
64
68
24
57
60
61
95
mg/1
»g/i
mg/1
mg/1
mg/1
mg/1
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
mg/1
mg/1
%
Recovery
89
93
93
98
97
94
88
98
96
81
102
99
99
92
103
95
100
96
97
103
103
104
-86-
C-3-40
-------
TABLE 43 (Cont.)
Ele- Sample
nent Identification
Pb 745CA 010-002 TMSA
746AT 008-002 TMSA
747HO 006-002 TMSA
748BA 002-002 TMSA
749SW 003-001 TMSA
7SOGO 010-002 TMSA
745CA 006-004 ELSA Rep 3
746AT 001-004 ELS A Rep 1
746AT 006-004 ELSA Rep 2
747HO 001-004 ELSA Rep 2
748BA 002-004 ELSA Rep 3
748BA 006-004 ELSA Sep 1
749SW 006-004 ELSA Rep 3
750GO 001-004 ELSA Rep 1
746AT 006-001 TMPA
750GO 006-001 TMPA
745CA 001-001 TMDA
749SW 006-001 TMDA
745CA 001-010 TMTB
746AT 005-009 TMTB
Concen-
tration
Added
3.65 mg/1
4.94 mg/1
4.11 mg/1
3.70 mg/1
4.61 mg/1
3.16 mg/1
50 ug/1
50 ug/1
50 ug/1
50 ug/1
50 ug/1
50 ug/1
50 ug/1
50 ug/1
111 ug/1
36 ug/1
133 ug/1
78 ug/1
25 ug/1
27 ug/1
Concen-
tration %
Recovered Recovery
3.26 mg/1
4. 55 rag/1
3.61 mg/1
3.39 mg/1
4.33 mg/1
2.77 mg/1
39 ug/1
47 ug/1
58 ug/1
63 ug/1
55 ug/1
44 ug/1
21 ug/1
50 ug/1
93 ug/1
34 ug/1
135 ug/1
84 ug/1
25 ug/1
28 ug/1
89
92
88
92
94
88
79
94
116
126
110
88
42
100
84
94
102
108
100
104
-87-
C-3-41
-------
TABLE 43 (Cont.)
Ele- Sample
ment Identification
Zn 745CA
746AT
747HO
748BA
749SW
750GO
74SCA
746AT
747HO
748BA
749SW
7SOGO
746AT
749SW
745CA
749SW
745CA
746AT
748BA
010-002
008-002
006-002
002-002
003-001
010-002
006-004
006-004
006-004
006-004
006-004
001-004
006-001
006-001
006-001
006-001
001-010
010-008
002-010
TMSA
TMSA
TMSA
TMSA
TMSA
TMSA
ELSA Rep 3
ELSA Rep 1
ELSA Rep 2
ELSA Rep 2
ELSA Rep 3
ELSA Rep 1
TMPA
TMPA
TMDA
TMDA
TMTB
TMTB
TMTB
5
6
4
4
5
4
3
3
3
Concen-
tration
Added
.24
.17
.99
.84
.86
.31
125
125
125
288
159
125
400
125
190
226
.65
.55
.95
mg/l
mg/1
mg/l
mg/1
mg/l
mg/l
ug/1
ug/l
ug/l
ug/l
ug/l
ug/i
ug/l
ug/l
ug/l
ug/l
mg/l
mg/l
mg/l
Concen-
tration
Recovered
5
5
4
5
5
4
-
3
3
4
.01
.88
.75
.68
.82
.05
122
136
141
289
166
141
399
125
201
225
.70
.88
.05
mg/l
mg/l
mg/l
mg/l
mg/l
mg/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
ug/l
mg/l
mg/l
mg/l
%
Recovery
96
95
95
97
99
94
98
109
113
100
104
113
100
100
106
100
101
101
103
-88-
C-3-42
-------
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TABLE 45
EVALUATION OF EXTRACTION EFFICIENCY OF PRECONCSNTRATION METHOD
FOR SEAWATER ANALYSES OF Cd, Or, Cu,
Kltaent
Cd
Cr
Cu
MB
Hi
Vb
Za
Sample
Identification
745CA 006-001 TMDA
747BO 006-001 TMQA
748BA 002-001 TMDA
748BA 006-001 TMOA
745CA 006-001 TMDA
747HO 006-001 TMDA
748BA 002-001 TMDA
748BA 006-001 TMDA
745CA 006-001 TMDA
747HO 006-001 TMDA
748BA 002-001 TMDA
748BA 006-001 TMDA
745CA 006-001 TMDA
747BO 006-001 TMDA
7488A 002-001 TMDA
748BA 006-001 TMDA
745CA 006-001 TMDA
747HO 006-001 TMDA
748BA 002-001 TMDA
748BA 006-001 TMDA
74SCA 006-001 TMDA
747BO 006-001 TMDA
748BA 002-001 TMDA
748BA 006-001 TMDA
745CA 006-001 TMDA
747HO 006-001 TMDA
74SBA 002-001 TMDA
748BA 006-001 TMDA
Concentration
Added (pg/1)
1.5
0.81
0.80
0.76
2.1
0.68
1.7
0.56
3.1
1.5
1.9
1.3
4.7
1.0
2.6 .
0.79
7.0
1.4
4.9
1.4
4.9
3.5
2.6
3.2
10.5
3.5
9.0
2.4
Mn, Hi, Pb, and
Concentration
Recovered (pg/1)
1.2
0.79
0.70
1.4
0.45
0.33
0.33
0.24
3.7
1.1
1.7
0.84
7.6
0.87
1.0
1.1
5.7
1.7
3.7
1.7
3.8
2.8
4.0
2.6
3.1
1.2
3.0
2.1
Zn
% Recovery*
111 + 50
33 + 15
87 * 24
107 + 55
99 + 25
98 + 37
46 + 28
Mean and standard deviation.
-90-
C-3-44
-------
Analyses of two National Bureau of Standards Reference
Materials (SRMs) are shown in Table 46. Analyses of NBS SRM
1645 (River Sediment) using the 1 N HN03 leach showed
excellent agreement with previous analyses. Analyses of
NBS SRH 1566 (Oyster Tissue) showed excellent agreement with
certified values for Cd, Cu, Hg, Mn, Pb, and Zn. Analyses for
Cr and Pb were less accurate due to under-recovery during
digestion or analytical variability. Arsenic recoveries
were excellent and showed a marked improvement over previous
analyses.
Analytical blanks for all metal analyses are shown in
Table 47.
-91-
C-3-45
-------
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3.2.2 Organohalogen Analyses
Table 48 shows recovery of organohalogens from the three
matrices of interest. Aroclor 12,21 was spiked as this is the
lightest of the PCS mixtures and recoveries of the other PCBs
should be comparable to or greater than those observed for
Aroclor 1221.
Recoveries of organohalogens from seawater are slightly
lower in some cases than those of Junk et al. (1974) who
reported recoveries ranging from 47% for Aldrin to 96% for DDT
using XAD-2 resin and aqueous samples. A duplicate spike for
single components showed excellent reproducibility. Spiked
sediment and tissue samples show acceptable recoveries with
the exception of methoxychlor.
Sample duplicate results are shown in Table 49. Sediment
duplication is complicated in the case of dieldrin by inter-
ference in the sample f-2. Due to our lower sensitivity for a
multicomponent mixture of PCBs relative to single component
pesticides such as pp'DDE, the PCSA Aroclor 1254 duplicate is
probably an accurate reflection of reproducibility as the
limits of our sensitivity are approached.
-94-
C-3-48
-------
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-95-
C-3-49
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-96-
C-3-50
-------
3.2.3 Total Organic Carbon Analyses
Quality control data associated with total organic
carbon analyses are shown in Table 50. Analyses of certified
reference materials agreed well with certified values.
3.2.4 Oil and Grease Analyses
Quality control data associated with oil and grease
analyses are shown in Table SI. Duplicate analyses
(Table Sla) showed reasonable agreement and spike recoveries
of SAE 10 crude oil averaged 88% (Table Sib).
3.2.5 Cyanide Analyses
Quality control data associated with cyanide analyses are
shown in Table 52. Recovery of cyanide spikes to sediments
are shown in Table 52a. Recovery of distilled cyanide spikes
(additions of cyanide to blank solutions which are processed
in a manner identical to sediment samples) are shown in
Table 52b. Recoveries of spike to elutriate samples are shown
in Table 52c. In all but two cases, recoveries were greater
than 80%.
-97-
C-3-51
-------
TABLE 50
RESULTS OF ANALYSES OF REFERENCE MATERIAL FOR TOTAL ORGANIC CARBON
Sample Identification TOC (mg/g)
LBCO-1
certified value 8.79 ^ 0.08
- Beaeured value 9.03
UCO-2
- certified value 0.51 + 0.02
neaeured value 0.48
-98-
C-3-52
------- |