wEPA
United States
Environmental Protection
Agency
Office of Water
(WH-556F)
EPA 842-S-92-011
June 1992
Final Report for 106-Mile
Deepwater Dumpsite
Winter 1988 Survey
RecycJed/Recydflbte
PnnUd on paper that contains
at least 50% recycled fiber
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FINAL REPORT
106-MILE DEEPWATER DUMPSITE
WINTER 1988 SURVEY
November 3, 1988
U.S. ENVIRONMENTAL PROTECTION AGENCY
Office of Marine and Estuarine Protection
Washington, DC
and
Region II
New York, New York
Prepared Under Contract No. 68-03-3319
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EXECUTIVE SUMMARY
The U.S. Environmental Protection Agency (EPA), under the Marine
Protection, Research, and Sanctuaries Act of 1972 (MPRSA, PL 92-532), is
monitoring the 106-Mile Deepwater Municipal Sludge Site (106-Mile Site). The
objective of the 106-Mile Site monitoring program is to ensure that provisions
of EPA's ocean dumping regulations are met through assessment of compliance
with permit conditions and assessment of potential impacts on the marine
environment. The program is being implemented according to a tiered approach,
whereby data collected in each tier are not only used in making site management
decisions but also are required as the foundation for the design and extent of
monitoring activities in the next (lower) tier. Four tiers are included in the
monitoring program: (1) Sludge Characteristics and Disposal Operations; (2)
Nearfield Fate and Short-Term Effects; (3) Farfield Fate; and (4) Long-Term
Effects.
This report presents the results from nearfield fate studies conducted at
the site in March 1988. Currently, dumping at the site is conducted under
court order. If permits for disposal of sludges are issued, they will
stipulate that water quality criteria (WQC) and limiting permissible
concentrations (LPC) may not be exceeded within the site four hours after
dumping or outside the site at any time. Nearfield fate determinations
address the horizontal and vertical behavior and movement of sludge within and
immediately adjacent to the site. Monitoring behavior and movement of sludge
immediately after disposal is necessary to confirm assumptions regarding
dispersion and dilution that were made in issuing permits. Nearfield fate
monitoring also addresses the potential for impacts within the immediate
vicinity of the site and in the short-term. This information will also be used
to guide monitoring activities to assess short-term biological effects of
sludge disposal.
The 106-Mile Site monitoring plan presents several hypotheses related to
nearfield fate of sludge plumes, and these hypotheses were tested during the
survey. Results from the survey indicated the following:
Permit Compliance
Ho3: Concentrations of sludge and sludge constituents outside
the site are below the permitted LPC and WQC at all times.
Because of low surface current drift at the site
during the time of the survey, sludge plumes
monitored at the site were not observed to cross
site boundaries during the March 1988 survey.
Analysis of transport suggests that water quality
criteria would not be exceeded outside the site
for these plumes.
One barge was found dumping outside of site
boundaries. Concentrations of sludge and sludge
constituents probably exceeded permitted levels
for this plume.
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H04; Concentrations of sludge and sludge constituents within
the site are below the permitted LPC and HQC 4 h after
disposal.
Concentrations of all sludge contaminants for
which there are marine WQC were below or
calculated to be below WQC 4 h after disposal, as
determined by analysis of water samples in
sludge plumes. Dilution rates of plume cores
(most concentrated parcels) calculated from
transmissometry suggest that had samples been
collected in the plume core of DB-13, WQC would
have been exceeded for it least copper and lead.
Therefore, at least for this plume, samples
collected for water quality analyses probably
were not representative of the most concentrated
volume in the plume and therefore HQC data for
this survey may have underestimated contaminant
levels at the site.
H05j Pathogen levels do not exceed ambient levels 4 h after
disposal.
The microbial tracer, C. perfrinqens, exceeded
ambient levels in the only sludge plume sampled
at T=4 h. C. perfrinqens is not a pathogen, but
a conservative microblal tracer of sewage;
therefore, C. perfringens data are not conclusive
proof that pathogen levels are being exceeded 4 h
after disposal. Measurements of C. perfringens
suggested that this hypothesis was false, direct
measurements of pathogens will be required to
prove it false.
Impact Assessmentt Nearfield Fate
H06: Sludge particles do not settle in significant quantities
beneath the seasonal pycnocline (50 m) or to the 50-m
depth at any time, within the site boundaries or in an
area adjacent to the site.
Sludge was observed to penetrate the surface
pycnocline (between shelf and slope waters) and
descend to 80 m within 3 h after dumping during
one dumping event. The deep penetration may
have been related to a dumping rate in excess of
the court-ordered 15,500 gal/min. Sludge dumped
at the court-ordered rate of 15,500 gal/min or
less was observed to remain within the upper 25 m
during winter oceanographic conditions. This
11
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hypothesis was therefore demonstrated to be false
under the observed conditions.
HO?: The concentration of sludge constituents within the site
does not exceed the LPC or HQC 4 h after disposal and is
nat detectable in the site I day after disposal.
As stated in Ho4, sampling and analysis of water
samples for sludge constituents was insufficient
to determine if ViQC were exceeded 4 h after
disposal.
Some surface water collected for background
contaminant analysis contained metal contaminant
levels approaching or exceeding HQC, The high
levels probably resulted from previous dumping
activity at the site, although this cannot be
verified from the data. In the absence of
surface currents that would remove surface
contamination, the frequency of dumping creates
the potential for contaminants to accumulate in
surface waters.
Although not observed, the rapid formation of
two fractions of sludge plumes (one containing
dissolved contaminants, the other containing
particulate matter) can be predicted from the
limited data set on dissolved and particulate
contaminants in sludge plumes. A plume of
dissolved contaminants would not disperse
rapidly under conditions observed at the site,
and the predicted presence of such a plume might
be the cause of the elevated contaminant levels
in background samples.
H
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Ho9: The disposal of sludge does not cause a significant
depletion in the dissolved oxygen content of the water nor
a significant change in the pH of the seawater in the
area.
The observed depression in dissolved oxygen
levels in sludge plumes is minor and at the
limit of instrument resolution. During the
winter survey, pH was not monitored in sludge
plumes.
Because of limitations associated with water quality measurements at the
site, the assessment of sludge plume behavior and transport under winter
conditions is considered incomplete. Sludge dispersion and transport data
indicate that under quiescent oceanographic conditions the settling and
dispersion of sludge in winter is similar to that observed during summer. The
preliminary results of this survey were used to plan appropriate measurements
of short-term effects of sludge dumping, and helped guide plans for assessing
farfield fate of sludge constituents.
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TABLE OF CONTENTS
1.0 INTRODUCTION . „ 1-1
2.0 SURVEY OBJECTIVES AND STRATEGY . 2-1
3.0 SAMPLE COLLECTION AND ANALYSIS METHODS 3-1
3.1 PHYSICAL OCEANOGRAPHIC MEASUREMENTS 3-1
3.1.1 HATER COLUMN PROFILING 3-1
3.1.2 CURRENT MEASUREMENTS 3-5
3.2 HATER QUALITY SAMPLE COLLECTION 3-6
3.2.1 HATER SAMPLES FOR TRACERS AND METAL
HATER QUALITY PARAMETERS.. 3-6
3.2.2 HATER SAMPLES FOR ORGANIC CONTAMINANTS 3-7
3.2.3 PROCESSING OF TRACER SAMPLES. 3-7
3.2.4 PROCESSING OF PARTICULATE MATTER 3-7
3.3 ENDANGERED SPECIES OBSERVATIONS.. 3-8
3.4 ANALYTICAL METHODS 3-8
3.4.1 TRACE METALS 3-10
3.4.1.1 Cadmium, Copper, Iron, Lead, Nickel,
and Zinc 3-10
3.4.1.2 Silver. .. 3-10
3.4.1.3 Chromium 3-10
3.4.1.4 Mercury 3-10
3.*,1.5 Selenium and Arsenic.. 3-11
3.4.2 ORGANIC COMPOUNDS 3-11
3.4.3 TOTAL SUSPENDED SOLIDS (TSS) 3-11
3.4.4 Clostridium Perfringens.... 3-12
4.0 RESULTS AND DISCUSSION 4-1
4.1 OCEANOGRAPHIC CONDITIONS 4-1
4.1.1 HATER MASS CHARACTERISTICS 4-1
4.1.1.1 CTD Transect to the 106-Mile Site. 4-2
4.1.1.2 Satellite Thermal Imagery .... 4-6
4.1.1.3 Hydrographic Conditions at the Site..... 4-8
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TABLE OF CONTENTS (Continued)
Page
4.1.2 NEAR-SURFACE CURRENTS 4-8
4.1.2.1 XCP Current Profile Results... 4-9
4.1.2.2 Near-Surface Drifter Results 4-10
4.2 BACKGROUND MATER QUALITY 4-12
4.3 BARGE DUMPING INFORMATION 4-15
4.4 SLUDGE PLUME BEHAVIOR 4-22
4.4.1 VERTICAL AND HORIZONTAL SPREADING 4-22
4.4.1.1 Vertical Spreading 4-23
4.4.1.2 Horizontal Spreading 4-27
4.4.2 SLUDGE DILUTION AND TRANSPORT 4-30
4.4.2.1 Dilution Based on Transmissometry Data 4-31
4.4.2.2 Estimation of Dilution Based on
Chemical Tracer Data........ 4-41
4.4.2.3 Plume Transport 4-45
4.5 WATER QUALITY MEASUREMENTS 4-47
4.5.1 COMPARISON TO HATER QUALITY CRITERIA , 4-47
4.5.2 ClostridiuiB perfringens 4-49
4.5.3 DISSOLVED OXYGEN....... 4-51
4.6 DISSOLVED AND PARTICULATE CONTAMINANT DISTRIBUTION 4-51
4.7 OBSERVATIONS OF CETACEANS AND MARINE TURTLES 4-56
5.0 CONCLUSIONS 5-1
5.1 DISCUSSION OF NULL HYPOTHESES....... 5-1
5.2 EVALUATION OF MEASUREMENT TECHNIQUES. 5-4
6.0 REFERENCES 6-1
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LIST OF TABLES
Page
TABLE 1-1. BARGES THAT DUHPED MUNICIPAL SEWAGE SLUDGE AT THE
106-MILE SITE DURING THE SURVEY OPERATIONS FROM
MARCH 2 THROUGH MARCH 4, 1988......... 1-7
TABLE 1-2. LIST OF PARTICIPANTS, WINTER 1988 OCEANOGRAPHIC SURVEY 1-8
TABLE 1-3. PARTICIPATING PERSONNEL, LABORATORY ACTIVITIES, AND
DATA ANALYSIS 1-9
TABLE 2-1. ELEMENTS AND COMPOUNDS FOR WHICH THERE ARE MARINE
MATER QUALITY CRITERIA 2-2
TABLE 2-2. MONITORING ACTIVITIES 2-4
TABLE 3-1. MEASUREMENT SPECIFICATIONS FOR CTD SENSORS 3-4
TABLE 3-2. OBJECTIVES FOR ANALYTICAL MEASUREMENTS OF WHOLE WATER
AND PARTICULATE SAMPLES... 3-9
TABLE 4-1. BACKGROUND WATER QUALITY MEASUREMENTS IN SEAWATER AT THE
106-MILE SITE, MARCH 2-4, 1988.. 4-13
TABLE 4-2. COMPARISON OF BACKGROUND WATER QUALITY MEASUREMENTS AT
THE 106-MILE SITE, SEPTEMBER 1987 AND MARCH 1988 4-14
TABLE 4-3. SUMMARY OF DUMPING METHODS, SLUDGE CAPACITY, AND ORIGIN OF
SLUDGE FOR EACH VESSEL DUMPING SLUDGE AT THE 106-MILE
SITE DURING THE PERIOD MARCH 2-4, 1988 4-18
TABLE 4-4. SUMMARY OF DUMPING INFORMATION FOR BARGES DUMPING SLUDGE
AT THE 106-MILE SITE DURING THE PERIOD MARCH 2-4, 1988 4-19
TABLE 4-5. SUMMARY OF TOTAL SUSPENDED SOLIDS CHARACTERISTICS FOR THE
SLUDGES SURVEYED DURING THE SEPTEMBER 1987 AND MARCH 1988
SURVEYS AT THE 106-MILE SITE 4-24
TABLE 4-6. SUMMARY OF PLUME DILUTION RATES BASED UPON TRANSMISSOMETRY
DATA FROM PROFILING SURVEYS IN MARCH 1988 (DB-13) AND
SEPTEMBER 1987 (DB-3 AND DB-4).. 4-40
TABLE 4-7. ESTIMATES OF INITIAL DILUTION FOR SEWAGE SLUDGE PLUMES
STUDIED IN MARCH 1988 4-42
TABLE 4-8. ESTIMATES OF ADDITIONAL DILUTION AFTER T=0 h DUE TO OCEANIC
MIXING FOR SEWAGE SLUDGE PLUMES STUDIED IN MARCH 1988 4-44
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LIST OF TABLES (Continued)
Page
TABLE 4-9. SUMMARY OF PLUME TRANSPORT INFORMATION FOR PLUMES
MONITORED DURING THE MARCH 1988 SURVEY AT THE 106-MILE
SITE 4-46
TABLE 4-10. COMPARISON OF METAL MEASUREMENTS IN SLUDGE PLUMES DB-2
AND DB-3 APPROXIMATELY 4 h AFTER DISPOSAL AT THE 106-
MILE SITE TO EPA MARINE WATER QUALITY CRITERIA 4-48
TABLE 4-11. CONCENTRATIONS OF C^ Perfrlngens IN THE SLUDGE PLUMES
AT T=0 h AND BETWEEN 6.5 AND 4 h AFTER DISPOSAL ..4-50
TABLE 4-12. COMPARISON OF PARTITIONING OF METALS BETWEEN DISSOLVED
AND PARTICULATE PHASES IN SLUDGE DUMPED AT THE 106-MILE
SITE 4-53
TABLE 4-13. PARTITIONING OF METALS BETWEEN DISSOLVED AND PARTICULATE
PHASES IN SLUDGE DUMPED AT THE 106-MILE SITE AT T=0 h
AND AT LEAST 1 h AFTER DISPOSAL 4-54
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LIST OF FIGURES
Page
FIGURE 1-1. LOCATION OF THE 106-MILE DEEPWATER MUNICIPAL SLUDGE SITE... 1-2
FIGURE 3-1. SCHEMATIC DIAGRAM OF SHIPBOARD DATA ACQUISITION SYSTEM 3-3
FIGURE 4-1. HAP SHOWING THE LOCATIONS OF THE R/V ENDEAVOR AT CTD
PROFILE STATIONS T-l, T-2, AND T-3, ALONG THE
SOUTHBOUND TRANSECT ON MARCH 1. 1988 4-3
FIGURE 4-2. COMPOSITE OF HYDROGRAPHIC PROFILE RESULTS FROM STATIONS
ALONG THE SOUTHBOUND TRANSECT TO THE 106-MILE SITE:
SIGMA-T PROFILES; BEAM ATTENUATION PROFILES; TEMPERATURE/
SALINITY CHARACTERISTICS... 4-4
FIGURE 4-3. VERTICAL TRANSECT OF HYDROGRAPHIC PROPERTIES ALONG THE
SOUTHBOUND TRANSECT TO THE 106-MILE SITE: TEMPERATURE;
SALINITY; DISSOLVED OXYGEN 4-5
FIGURE 4-4. OCEAN FRONTAL ANALYSIS OF THE U.S. EAST COAST FOR
FEBRUARY 29, 1988, DERIVED FROM SATELLITE THERMAL IMAGERY.. 4-7
FIGURE 4-5. SUMMARY OF NEAR-SURFACE DRIFTER RESULTS FROM PLUME EVENTS
OB-10 AND DB-11 AND DB-13 AND DB-14 DURING THE MARCH 1988
SURVEY AT THE 106-MILE SITE 4-11
FIGURE 4-6. COMPARISON OF DATA FROM BACKGROUND STATIONS SAMPLED AT THE
106-MILE SITE IN SEPTEMBER 1987 AND MARCH 1988; TOTAL
SUSPENDED SOLIDS, TOTAL COPPER, AND TOTAL IRON 4-16
FIGURE 4-7. PLOT OF VOLUME DUMPING RATE (gal/Bin) VERSUS BARGE SPEED.. 4-21
FIGURE 4-8. TIME SERIES PLOT OF PLUME THICKNESS FOR PLUMES SURVEYED
IN SEPTEMBER 1987 AND MARCH 1988 4-25
FIGURE 4-9. TIME SERIES PLOT OF PLUME WIDTH FOR PLUME EVENTS DB-10
AND DB-12 SURVEYED IN MARCH 1988 4-29
FIGURE 4-10. TIME HISTORY OF SLUDGE DILUTION FOR PLUME EVENT DB-3
DURING SEPTEMBER 1987 4-32
FIGURE 4-11. COMPOSITE OF TURBIDITY (BEAM ATTENUATION) ANALYSES FOR
INDIVIDUAL VERTICAL PROFILES OF PLUME EVENT DB-3 IN
SEPTEMBER 1987 4-34
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LIST OF FIGURES
Page
FIGURE 4-12. COMPOSITE OF TURBIDITY (BEAM ATTENUATION) ANALYSES FOR
INDIVIDUAL VERTICAL PROFILES OF PLUME EVENT DB-13 IN
MARCH 1988 . 4-36
FIGURE 4-13. COMPOSITE OF TURBIDITY (BEAM ATTENUATION) ANALYSES WITHIN
THE CORE OF THE PLUME FOR EVENTS DB-3. DB-4, AND DB-13..,. 4-37
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1.0 INTRODUCTION
Under the Marine Protection, Research, and Sanctuaries Act of 1972
(MPRSA, PL 92-532), the U.S. Environmental Protection Agency (EPA) is
responsible for regulating disposal of wastes, including sewage sludges, in
ocean waters. Under this authority, EPA has published ocean dumping
regulations (40 CFR Parts 220-229) that specify procedures for monitoring
ocean dumpsites. EPA's responsibility for developing and maintaining
monitoring programs for designated ocean disposal sites is described in
these regulations.
In carrying out the responsibility for developing monitoring
programs, EPA has prepared a monitoring plan for the 106-Mile Deepwater
Municipal Sludge Site (106-Mile Site) ( EPA , 1992a). The site is located
off the coast from New York and New Jersey (Figure 1-1). Data generated by
the program will be used by site managers to make decisions about site
redesignation or dedesignation; continuation, termination, or modification of
permits; and continuation, termination, or modification of the monitoring
program itself.
The objective of the 106-Mile Site monitoring program is to ensure
that the regulations are met through assessment of compliance with permit
conditions and assessment of potential impacts on the marine environment.
The program is being implemented according to a tiered approach, whereby data
collected in each tier are not only used in making site management decisions
but are also required as the foundation for the design and extent of
monitoring activities in the next (lower) tier. Four tiers are included in
the monitoring program: (1) Sludge Characteristics and Disposal Operations;
(2) Nearfield Fate and Short-Term Effects; (3) Farfield Fate; and (4) Long-
Tertn Effects.
Nearfield fate studies being conducted under Tier 2 of the
monitoring program address both the permit compliance and the impact
assessment components of monitoring at the site. Currently, dumping at the
site is conducted under court order. When permits for disposal of sludges
are issued, they will stipulate that water quality criteria (WQC), where they
exist, may not be exceeded within the site 4 h after dumping or outside the
site at any time. When WQC do not exist, the permits will require that the
1-1
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106—Mil» D*»pwat*r
Municipal Studg* Site
FIGURE 1-1. LOCATION OF THE 106-MILE DEEPWATER MUNICIPAL SLUDGE SITE.
1-2
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concentration of the sludge not exceed a factor of 0.01 times a concentration
known to be acutely toxic after initial mixing, i.e., the limiting
permissible concentration (LPC). The combined conforaance to LPCs and WQC is
thought to be protective of the marine environment.
Nearfield fate monitoring also addresses the potential for impacts
within the immediate vicinity of the site and in the short term, defined for
convenience as 24 h. Nearfield fate determinations address the horizontal
and vertical behavior and movement of sludge within and immediately adjacent
to the site. Monitoring behavior and movement of sludge immediately after
disposal is necessary to confirm assumptions regarding dispersion and
dilution that will be used in issuing permits. This information will also be
used to guide monitoring activities to assess short-term biological effects
of sludge disposal.
The 106-Mile Site monitoring plan presents the following hypotheses
related to nearfield fate of sludge plumes;
Permit Compliance
H03: Concentrations of sludge and sludge constituents outside the
site are below the permitted LPC and WQC at all times.
Ho4: Concentrations of sludge and sludge constituents within the
site are below the permitted LPC and WQC values 4 h after
disposal.
H05s Pathogen levels do not exceed ambient levels 4 h after
disposal.
Impact Assessment
H0fij Sludge particles do not settle in significant quantities
beneath the seasonal pyenocline (50 m) or to the 50-m depth at
any time, within the site boundaries or in an area adjacent to
the site.
H07: The concentration of sludge constituents within the site does
not exceed the LPC or WQC 4 h after disposal and is not
detectable in the site 1 day after disposal.
1-3
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Ho8: The concentration of sludge constituents at the site boundary
or in the area adjacent to the site does not exceed the LPC or
WQC at any time and is not detectable 1 day after disposal.
H09: The disposal of sludge does not cause a significant depletion
in the dissolved oxygen content of the water nor a significant
change in the pH of the seawater in the area.
The activities being conducted under Tier 2 have been selected to
test these hypotheses. These activities include direct studies of sludge
plumes under varied oceanographic and meteorological conditions.
Specifically, Tier 2 includes the following activities designed to assess
nearfield fate, as described in an implementation plan that supplements the
monitoring plan for the site ( EPA , 1992b);
Rerant Compliance
Measure sludge constituents in the water column to determine fate
of sludge constituents, with respect to permit conditions and
ambient conditions. Measurements of water quality, and chemical
and microbiological parameters are being made to determine whether
concentrations of sludge constituents meet permit conditions and
are at background levels within 1 day after disposal. These
measurements address null hypotheses 3 through 5 and 7 through 9.
Impact Assessment
Conduct sludge plume observations to define the seasonal patterns
of sludge dispersion at the 106-Mile Site. Nearfield fate studies
include use of a variety of methods to track sludge plumes under
summer and winter conditions. These studies are being used to
determine when and where samples should be taken, when and where
the sludge plume crosses the site boundary, and where to sample to
determine whether sludge constituents are detectable 1 day after
disposal. They also provide information on whether sludge
particles settle beneath the pycnocline. The studies provide
information to guide sampling for sludge constituents in the water
column and also address H06.
Preliminary observations of plume transport at the site were made
during an EPA survey of the site in September 1986 ( EPA , 1988a). Visual
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observations and measurements of sludge tracers (total suspended solids and
spores of the microbe Clostridium perfrlngens) indicated that sludge plumes
could be tracked to the boundaries of the 106-Mile Site. These preliminary
observations indicated that there is a potential for violating permit
conditions and for adverse short-term impacts from disposing sludge at the
site.
EPA then developed a strategy for comprehensive assessment of
nearfield, short-term fate of sludge constituents ( EPA , 1987a). This
strategy outlined a plan for assessing various methods of tracking sludge
plumes and for measuring compliance with expected permit conditions. It
presented the following specific information to be obtained during nearfield
fate monitoring at the site:
Penait Compliance
* Determination of whether sludge constituents for which there
are WQC are present in concentrations above the WQC within the
site boundaries within 4 h after dumping and outside the site
boundaries at any time.
• Determination of whether concentrations of the microbe
Clostridium perfringens exceed ambient levels within the site
4 hafter disposal.
Impact Assessment
* Determination of the dilution of sludge in seawater
immediately upon dumping and during the first hour after
dumping.
• Determination of the short-term effects of sludge on the
dissolved oxygen levels at the site.
• Determination of the rate and direction of movement of the
surface and subsurface expression of the plume within the
site.
• Determination of the extent of horizontal dispersion of the
plume.
* Determination of the extent of vertical dispersion of the
dissolved and participate components of the plume.
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Determination of the effect of a seasonal pycnocline on the
settling of sludge.
Surveys addressing these issues were conducted at the 106-Mile Site
in September 1987 and again in March 1988. Results of the September 1987
survey have been described previously ( EPA , 19i2c)» Results of the March
1988 survey are presented in this report. Chapter 2 presents the strategy for
making nearfield fate measurements of sludge constituents and tracers of sludge
plumes. Chapter 3 describes the sample collection and analysis methods.
Chapter 4 describes the oceanographic conditions in the region of the site at
the time of the survey and presents the results of the analyses. The
conclusions of the study, including an assessment of behavior and transport of
plumes in terms of the null hypotheses and a comparison to the September 1987
survey, are presented in Chapter 5.
The survey was conducted from March 1 to March 5, 1988 on board the
Reasearch/Vessel (R/V) Endeavor operated by the University of Rhode Island.
The survey was mobilized and demobilized out of Narragansett, Rhode Island.
The survey monitored six plumes, identified as DB-10 through DB-15, on March 2
through 4, 1988 (Table 1-1). A complete description of the survey is presented
in the initial survey report and in the site condition report for the survey
( EPA , 1988b and 1988c).
Key personnel involved in this work assignment included Frank Csulak,
EPA Co-Work Assignment Manager and Chief Scientist for the survey,* Barry
Burgan, EPA Co-Work Assignment Manger; Christine Wenne, Technical Monitor;
William Steinhauer, Work Assignment Leader; Scott McDowell, Chief Battelk
Scientist for the survey; and Carl ton Hunt, Task Manager for all laboratory
activities.
Survey participants are listed in Table 1-2. Individuals involved in
laboratory activities and data analysis are presented in Table 1-3. William
Steinhauer, Scott McDowell, Carlton Hunt, and Christine Werme authored this
report.
1-6
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TABLE 1-1. BARGES THAT DUMPED MUNICIPAL SEWAGE SLUDGE AT THE 106-MILE
SITE DURING THE SURVEY OPERATIONS FROM MARCH 2
MARCH 4, 1988.
Pluae
Surrey
DB-10
DB-11
DB-12
D8-13
DB-14
D8-15
Tug Barge
Sheila Moran Lemon Creek
Emily-S Leo Frank
Elizabeth Weeks 701
Kate Morris Berman
Esther Moran Spring Creek
OBI4
Dumping
(h)
1212
1614
2011
2303
0712
0950
2006
2223
0719
0922
1102
1133
Time
3/2 to
3/2
3/2 to
3/2
3/3 to
3/3
3/3 to
3/3
3/4 to
3/4
3/4 to
3/4
1-7
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TABLE 1-2. LIST OF PARTICIPANTS, WINTER 1988 OCEANOGRAPHIC SURVEY
EPA REGION II
Frank Csulak
Joseph Hudek
Chief Scientist
Dye Studies
BATTELLE
Scott McDowell
Carl ton Hunt
Wayne Trulli
Carl Albro
Jeffery Waugh
Deborah West
Felicia Giordano
Charles Willauer
Task Leader, XCPs, Aerial
Reconnaissance
Vertical Profiling and Sampling
Sampling and Sample Tracking
CTD, Computer Support
Sampling
Sampling
Microbiology
Navigation
MAHOMET BIRD OBSERVATORY
Burt Nickerson
Endangered Species Observations
NEW YORK DEPARTMENT OF ENVIRONMENTAL PROTECTION
Thomas Brosnan
Sampling
UNIVERSITY OF RHODE ISLAND.
GRADUATE SCHOOL OF OCEANOGRAPHY
Viva Banzon
Sampling, Microbiology
1-8
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TABLE 1-3. PARTICIPATING PERSONNEL, LABORATORY ACTIVITIES, AND DATA ANALYSIS.
Chemical Analysis
Carlton Hunt
Dion Lewis
Carole Peven
Debbie West
larisa Altshul
George Desreuisseau
Bernadette Koczwara
Task Manager, Chemical Analyses
and Interpretation
Subtask Leader, Inorganic Analyses
Subtask Leader, Organic Analyses
Inorganic Analyses
Organic Analyses
Organic Analyses
Organic Analyses
Physical Oceanoqraphic Data Analyses
Scott McDowell
Carl Albro
Charles Hillauer
Task Manager, Physical
Oceanographic Data Analyses
Data Analysis
Data Analysis
1-9
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2.0 SURVEY OBJECTIVES AND STRATEGY
The objectives of the survey of the 106-Mile Site were to employ a
variety of methods to (1) assess the movement, dilution, and settling of
sewage sludge as sludge plumes are transported towards and beyond the site
boundary, and (2) determine whether water quality requirements that will be
included in permits for dumping at the site are being met during ongoing
disposal operations. The survey was the second field application of
proposed technical methods for nearfield fate monitoring at the 106-Mile
Site, and the first to be conducted under winter conditions. Therefore, an
additional objective was to test equipment and protocols for future nearfield
fate monitoring activities that may be conducted by EPA or by permittees.
EPA strategy to accomplish these objectives involved conducting the
following activities in the survey:
* Identification and tracking of a sludge plume with dye
and surface and subsurface drogues.
* Monitoring of the movement and dispersion of the marked
sludge plume with visual observations from the R/V
Endeavor and an aircraft.
* Acquisition of in situ transmissometry data to monitor
the movement and dispersion of the plume.
• Collection of samples for analysis of chemical and
biological tracers and total suspended solids (TSS) to
- determine actual concentrations of sludge components and
dilution of these components.
* Collection of samples for analysis of those contaminants
that have marine water quality criteria {Table 2-1) to
determine water quality in the plume 4 h after disposal,
or at the site boundary if the sludge leaves the site
before 4 h.
* Acquisition of data to determine oceanographic conditions
at the site that may affect the movement of sludge.
These data included satellite-derived ocean frontal
analyses; conductivity/temperature/depth (CTD) profiles;
and current shear measurements.
* Acquisition of real-time navigation data to support
plume-tracking activities.
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TABLE 2-1, ELEMENTS AND CONFOUNDS FOR WHICH THERE ARE MARINE
HATER QUALITY CRITERIA.*
Inorganic Elements Arsenic
Cadmi urn
Chromium (hexavalent)
Copper
Cyanide
Lead
Mercury
Nickel
Selenium
Silver
Zinc
Organic Compounds Aldrin/Dieldrin
Chlordane
ODT and Metabolites
Endosulfan
Endrin
Heptachlor
PCBs
Toxaphene
aA11 samples on this work assignment were analyzed for total chromium instead
of hexavalent chromium. Cyanide was not analyzed.
2-2
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* Observations of endangered species of cetaceans, marine
turtles, and seabirds, according to EPA policy to
evaluate these animals on all surveys of the 106-Mile
Site.
These activities were grouped into major survey activities. A sumnary of
the major nearfield fate monitoring activities is presented in Table 2-2.
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TAiLE 2-2. MONITORING ACTIVITIES.
Activity Subactivity
Transect CTD Profiles None
Shakedown Exercises Testing of all oceanographic gear.
Activities include vertical profiling with CTD/
transmissometer and collection of water samples
for WQC contaminants.
Vertical Profiling CTD/transmissometer vertical profiling;
collection of discrete wattr samples for tracers,
metal WQC samples, TSS, and C. perfringens;
collection of water for organic WQC samples with
pumping system (surface) and Bodman bottles (50
m); XCP profiling.
Horizontal Profiling Towed fish with CTD/transmissometer, transmis-
someter,' XCP profiling.
2-4
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3.0 SAMPLE COLLECTION AND ANALYSIS METHODS
The primary method for the nearfield monitoring of sludge plumes
was use of transmissometry, which measured turbidity resulting from high
levels of total suspended solids In sludge. Real-time acquisition of
conductivity, temperature, depth, transraissometry, and dissolved oxygen data
resulted in large amounts data from horizontal profiles. The same in situ
data were acquired during vertical profiles which were augmented by the
collection of water samples for chemical and microbiological tracers and
marine water quality parameters. However, unlike the previous survey in
which chemical tracer and microbiological samples were collected with a
pumping system, the samples on the winter survey were collected using
individual sampling bottles. Surveying operations were also supported with
aerial photoreconnaissance. The aerial photoreconnaissance provided
information on lateral plume spreading and plume orientation.
The most obvious improvement in this survey over the previous
nearfield fate monitoring survey was the use of the real-time navigation
system developed for the survey. Acquisition and display of real-time
navigation data provided data critical for maneuvering the vessel during
nearfield fate profiling and provided excellent support for the other
measurements made during the survey. The necessity of this navigation
support on all future monitoring surveys at the 106-Mile Site was
demonstrated.
3,1 PHYSICAL OCEANOGRAPHIC MEASUREMENTS
Physical oceanographic data were acquired during the survey by
obtaining vertical and horizontal profiles of water column parameters,
obtaining vertical profiles of surface currents, and deploying near-surface
drifters.
3.1.1 Water Column Profiling
Vertical and horizontal water column profiling was performed with a
Sea-Bird Electronics conductivity-teiperature-depth (CTD) system interfaced
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to an IBM-PS/2 personal computer. A Sea-Bird Electronics dissolved oxygen
sensor and a Sea Tech 25-cra pathlength transmissometer were also interfaced
to the CTD underwater unit for concurrent, in situ measurements of oxygen and
turbidity (derived from percent light transmission). The CTD underwater unit
and sensor package was attached to the lower side of a 3-foot (wingspan)
Endeco V-Fin depressor.
The CTD underwater unit transmitted digital information to a deck
control unit via a Kevlar electromechanical (E/M) profiling cable. The CTD
deck control unit passed the raw CTD data to the computer of the shipboard
data acquisition system for real-time display and data storage. A Morthstar
Model 7000 Loran-C receiver was also interfaced to the computer system to
obtain and record vessel position information (Loran-C time delays, latitude,
and longitude) at 6-second intervals during surveying operations. Figure 3-1
illustrates the hardware configuration of the hydrographic data system
developed by Battelle for the operations. Measurement specifications for
each of the sensors are presented in Table 3-1.
Following the survey, binary data files of the digital CTD data
were returned to the laboratory for processing and review. The package for
processing CTD data from vertical profiles and horizontal tows was used to
perform the following functions:
* Conversion of raw (binary) CTD data into engineering
ynits: depth (m), temperature (°C), salinity (ppt),
oxygen (mL/L), and light transmission (percent light
extinction).
• Removal of data points that lie outside reasonable, site-
specific ranges for each measurement parameter.
• Retention of data points only when the depth series is
monotonically increasing (because good quality CTD data
can only be obtained when the sensors are descending
through the water column and passing through undisturbed
water).
For CTD data files acquired during horizontal profiling operations,
the processing procedures were identical to those described above, except
that data were not excluded on the basis of depth changes because the sensors
are continually towed through undisturbed water.
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Loran-C
Navigation
Computer
CTD
Deck Unit
E/M
Cable
V-Fin
CTD
Profiler
Depth
Plotter
Printer
Disk Storage
Monitor
Underwater
Unit
Temperature
Salinity
Dissolved Oxygen
Turbidity
FIGURE 3-1. SCHEMATIC DIAGRAM OF SHIPBOARD DATA ACQUISITION SYSTEM
3-3
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TABLE 3-1. MEASUREMENT SPECIFICATIONS FOR CTD SENSORS.
Parameter Range Accuracy Resolution
Depth
Temperature
Salinity
Oxygen
Light Transmission
0 to 3000 m
-5 to 35°C
0 to 40 ppt
0 to 15 ml/L
0 to 100 %
+60 cm
+O.Q04°C
+0.005 ppt
+0.1 mt/L
+0.5 %
12 cm
0.0003°C
0.0005 ppt
0.01 ml/I
0.01 %
Sampling rate: 24 samples per second (averaged to 8 samples per
second).
Vertical resolution during profiling! ~4 cm for 20 m/min lowering speed.
Horizontal resolution during towing: ~20 cm at 3-knot ship speed.
3-4
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Additional information regarding the configuration of the CTD, and
acquisition and reduction of these data is found in EPA (1992c).
3.1.2 Current Measurements
Vertical profiles of horizontal currents in the upper 1500 m of the
water column were acquired using an expendable current profiling (XCP) data
acquisition system and XCP probes manufactured by Sippican Ocean Systems.
The XCP data acquisition system consisted of a Hewlett-Packard Model 9816
microcomputer, an XCP controller unit containing a radio receiver, and a
radio antenna mounted on the upper deck of the survey vessel. For profiling
operations, an XCP probe was launched behind the vessel and data were
transmitted via the radio link to the on-board XCP data acquisition system.
During each profile, which lasted roughly 6 minutes, engineering information
was stored in computer memory for near real-time analysis. After the profile
cycle was complete, a processing program was used to convert the raw data
into engineering units of current speed, current direction, and water
temperature versus depth. These results were plotted within one half hour
after the launch to provide information on current shear in the upper water
column that would affect plume advection and tracking operations. XCP data
were stored on floppy disks for easy access from analysis programs.
Near-surface drifters, designed to maximize the cross-sectional
area of the drogue while minimizing the surface area and windage of the
surface markers, were fabricated specifically to track sludge plumes. For
each nearfield fate event except DB-12, one "shallow" drifter was deployed
with a drogue tethered 5 m below the surface. These drifters remained with
both the surface expression of the sludge plumes and the dye released within
the plumes for periods of several hours. A "deep" drifter, having a drogue
tethered at a depth of 50 m, was deployed alongside a shallow drifter during
plume events 08-10 and DB-14 to observe the currents beneath the seasonal
pycnocline. Except for DB-12, the sludge plumes were apparently confined to
the upper 20 m of the water column in the short-term, and there was no
operational need for tracking water beneath the pycnocline.
Drifters were tracked visually from the survey vessel. During
vertical profiling operations, the vessel would periodically stop alongside
the drifter to obtain a Loran~C position. During horizontal profiling,
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drifter positions were obtained when the vessel passed the drifter during
repeated transects of the plume. All Loran-C drifter positions and times
were recorded by the computer system used to acquire the hydrographic data.
For each drifter, a file of positions and times was archived to facilitate
analyses of trajectories and current vectors.
3.2 MATER SAMPLE COLLECTION
3.2.1 Hater Samples for Tracers and Metal Mater Quality Parameters
Collection methods for water samples for metals analysis were
different than those employed during the summer survey ( EPA , 1992c).
The sampling strategy was modified because under winter oceanographic
conditions the sludge was expected to descend to depths beyond the ability of
existing pumping systems. Additionally, rough winter seas were expected to
interfere with the use of the existing deck-mounted pumping system.
Go-Flo bottles directed by real-time CTD/transmissoraetry data were
used to collect metals and tracer water samples because this system had a
high probability of successfully returning samples from plumes that descend
deep into the water column. Two systems were developed to enable collection
of samples from the water column between 0 and 5 m, and between 0 and 100 m.
For collection of surface samples between 0 and 5 m, two Go-Flo bottles were
attached to a frame containing a small CTD and 25-cm-pathlength
transmissometer. For collection of samples from below 5 m, Go-Flo bottles
were attached to the electromechanical cable used to deploy the V-fin housing
the Seabird CTD/transmissometer system. For both systems, the Go-Flo bottles
were closed using messengers.
The sampling strategy was to collect all metals and tracer water
samples in the particle maximum as determined from the real-time display of
in situ parameters from the CTD profiling system. However, difficulties in
deploying, triggering, and retrieving bottles, and the rapid movement of the
ship' relative to the sludge plume limited the practicality of the strategy
for sampling sludge plumes. Also, correlating sample collection to
transmissometry observations proved more difficult than anticipated because
time of bottle closure could not be electronically verified on deck.
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Samples from the Go-Flo bottles were processed for laboratory trace
metal and total suspended solids (TSS) analysis, and for shipboard (X
perfringens enumeration. Samples for TSS were used for analysis of
particulite metal concentrations in the plume.
3.2,2 Mater Samples for Organic Contaminants
Large-volume organic samples were collected using two techniques.
For samples from depths greater than 5 m, 100-L aluminum sampling bottles
(Bodman bottles) were used. Samples from the ocean surface were collected
using a high-volume pumping system. Water collected by both methods was
transferred immediately to deck-mounted 100-L extraction containers.
Extractions were performed on board within 4 h of sample collection
( EPA , 1992c).
3.2.3 Processing of Tracer Samples and C. perfringens
Samples for analysis of sludge tracers and water quality parameters
were processed by removing samples from the Go-Flo bottles under nitrogen
pressure. Samples for analysis of C. perfringens were collected before those
for analysis of metal tracers. If a sample for mercury analysis was
required, it was collected after the metal tracer sample. All water quality
and metal tracer samples were acidified on board the survey vessel. Samples
for C. perfringens were processed on board as outlined in EPA (1992c).
3.2.4 Processing of Participate Hatter
Samples for analysis of total suspended solids (TSb) and particulate
trace metals were collected from the Go-Flo bottles after whole-water tracer
samples were collected. The samples were filtered directly from the Go-Flo
bottles using nitrogen pressure filtration. Seawater was forced at a
constant pressure of 5 psi through a Teflon tube attached to an in-line
filter holder containing a 47-mm 0.4-jnn Nuclepore filter. The amount of
seawater passing the filter was determined volumetrically. Filtering was
stopped when seawater no longer passed the filter. All filters were then
3-7
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rinsed with three 10 ml rinses of deionized water adjusted to pH 8 with
HH40H. All processing was conducted at a Class-100 clean bench.
3.3 ENDANGERED SPECIES OBSERVATIONS
Because of concern for the possible impact of ocean dumping
activities on endangered or threatened species of marine mammals and turtles,
the presence of these species in the area was recorded. Observations were
made by a qualified observer on the R/V Endeavor. These observations were
recorded along predetermined survey paths in 15-min periods, where each
period represented a transect.
The data were recorded in two major categories--
location/environmental and species/behavior. Information in each category
was recorded for each 15-min observation period and both categories were
identified by a unique survey and observation number. Location/environmental
data included latitude-longitude, start time, elapsed time, vessel speed and
course, water depth and temperature, barometric pressure trend, visibility,
and wind direction and speed. Species/behavior data included taxonomic
group, species identification, number of animals observed, age, distance and
angle to sightings, heading, animal association, debris association, and
behavior.
3.4 ANALYTICAL METHODS
Summaries of the data requirements for shipboard and laboratory
analytical methods are presented in Table 3-2. Quality control methHs used
to verify the accuracy and precision of these methods are presented in the
work/quality assurance project plan for this work assignment ( EPA ,
1992d). Results of the laboratory analytical quality control program are
discussed in Appendix A and presented in Tables A-l through A-8 in Appendix
A. Analytical methods are presented below.
3-8
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TABLE 3-2. OBJECTIVES FOR ANALYTICAL MEASUREMENTS OF WHOLE HATER AND PARTICULATE SAMPLES,
I
10
Laboratory Analyses*
Parameter, Units
Filtrate or ^articulates
WQC Organ ics /*g/L
Metals
Filtrate
Cr ng/l
Cd, Cu, Fe, Pb, Zn /*g/L
As, Se pg/L
Total Hg pg/L
Particulate
Metals mg/L
TSS rag/L
Detection
Limit
.0001-. 005
.015
.030
.015-. 030
.050
.0015
.01-. 5
.01
Accuracy
50
50
50
50
50
50
50
30
Precision
100
30
30
30
30
30
30
30
Method
Solvent Extraction, GC/ECD
Chelation-extraction pH 1.8, GFAA
Chelation-precipitation, GFAA
Chelation-extraction, GFAA
Hydride generation AA
Cold vapor AA
Acid digestion, GFAA
Filtration, gravimetric
SOPb
6-08
New Method
6-04
6-05
New Method
6-03
New Method
New Method
^Precision and accuracy of laboratory results addressed as percent of true values.
^Refers to EPA-approved SOPs for analytical procedures in support of the 106-Mile Site monitoring program (Battelle 1987b)
-------
3.4.1 Trace Metals
Methods for the extraction and analysis of trace metals are
summarized below.
3.4.1.1 Cadmium. Copper, Iron. Lead. Nickel, and Zinc
Unfiltered seawater samples were extracted at pH 5 with a 1 percent
solution of purified anrnoniura-1-pyrrolidine dithiocarbamate diethyl ammonium
diethyldithiocarbaraate (APDC-ODDC) and Freon (Danielsson et al., 1182). Each
sample was extracted three times with 5-nL aliquots of Freon; all Freon
extracts were combined. The metals were back-extracted into 2 ml of 10
percent nitric acid. The nitric acid solutions were analyzed for cadmium,
copper, iron, lead, nickel, and zinc by graphite furnace atomic absorption
spectrometry (GFAAS) with Zeeraan background correction.
3.4.1.2 Silver
Unfiltered seawater samples were extracted at pH 1.8 using the
APDC-DDDC procedure outlined above. Silver was analyzed using GFAAS.
3.4.1.3 Chromium
Total chromium was determined using a modification of the methods
described by Cranston and Murray (1977). Chromium was coprecipitated with
0.01 N Fe(OH)2 after an aliquot of seawater was adjusted to pH 8 with NfyOH.
The resulting precipitate was filtered and digested with 6 N nitric acid.
After dilution with deionized water to a known volume, the acid digests were
analyzed for total chromium by GFAAS.
3.4.1.4 Mercury
Mercury in seawater was determined according to the method of Gill
and Fitzgerald (1987), Mercury in a known volume of seawater was reduced
with starmous chloride in a closed vessel. The sample was purged with
nitrogen and the resulting elemental mercury was concentrated on gold-coated
3-10
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quartz sand. Using heat, the amalgamated mercury was quantitatively desorbed
from the gold trap into a stream of helium and analyzed with a Laboratory
Data Control UV mercury monitor.
3.4.1.5 Seleniua and Arsenic
Selenium and arsenic were determined by hydride generation of
aliquots of unfiltered seawater. Selenium and arsenic were reduced with a 3
percent solution of sodium borohydride. The elements were subsequently
purged from the sample into a heated quartz cell and quantified by AAS.
3.4.2 Organic Compounds
High-volume seawater samples (100 L) were extracted with 4 L
dichloromethane (DCM) in 150-L stainless steel extraction vessels on board
ship. The solvent layer was removed and the aqueous sample was reextracted
twice with 2-L aliquots of DCM. Extracts were shipped to the laboratory for
analysis. In the laboratory, the extracts from each sample were combined and
reduced in volume. Concentrated extracts were fractionated on silica-alumina
columns to remove matrix interferences.
Pesticides and polychlorinated biphenyls (PCBs) were analyzed by
electron capture detection capillary column gas chromatography (GC-ECD)
{ EPA , 1987b), Response factors for each compound were determined
relative to the internal standard dibromooctafluorobiphenyl. Field and
laboratory recoveries were determined through the use of surrogate materials.
All analytes reported were confirmed using the second column approach.
3.4.3 Total Suspended Solids (TSS)
In the laboratory, samples were air dried in a Class-100 clean room
and the mass of the loaded filter determined. The concentration of TSS was
calculated based on the weight of solids collected on the filter divided by
the volume of seawater filtered ( EPA , 1987c).
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3.4.4 Clostrldlua perfringens
Enumeration of C. perfringens in seawater was performed according
to the methods of Bisson and Cabelli (1979). C« perfringens spores were
collected by filtering 0.1-, 0.5-, and 1-L aliquots of seawater through
0.4-0m polycarbonate filters immediately after collection. The filters were
cultured anaerobically on modified C. perfringens (m-CP) medium.
Confirmation was obtained by exposing the incubated plates to ammonium
hydroxide vapors, which turn C. perfringens colonies a magenta color. The
bacteria were quantified as number of colonies per 100 ml of filtered
seawater.
3-12
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4.0 RESULTS AND DISCUSSION
Results of the March 1988 survey are presented and discussed in
this section. The results are discussed in terms of the background physical
oceanographic characteristics of the site at the time of the survey (Sections
4.1 and 4,2). Sludge spreading and mixing are then discussed (Sections 4.3
and 4.4). Impacts of sludge dumping on water quality are presented in
Section 4.5. Finally, results of the cetacean and marine turtle survey are
presented in Section 4.6.
4.1 OCEANOGRAPHIC CONDITIONS
4.1.1 Hater Mass Characteristics
The hydrographie data acquired during the survey represent a high-
resolution data set that is ideal for analyses of water mass characteristics
and mixing. These data, which include water temperature, salinity, density,
dissolved oxygen, and turbidity, were acquired with the high-resolution
conduct ivity/tentperature/depth (CTD) profiling system described in Section 3.
These data were analyzed in a variety of ways to provide information relevant
to the objectives of the survey. The specific hydrographie analyses are
listed below:
Analyses of the vertical density structure as it relates
to mixing of sludge plumes discharged at the 106-Mile
Site.
Analyses ^f temperature/salinity data for identification
of shelf water, slope water, and Gulf Stream warm-core
eddies in the vicinity of the site.
Comparisons between shipboard observations of water mass
boundaries and those derived from satellite thermal
imagery,
Analyses of background oxygen and turbidity
characteristics at the site for comparison with water
properties within sludge plumes.
Oceanographic characterization of the site to allow
comparisons with past and future surveys, and which can
4-1
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ultimately lead to seasonal descriptions of the 106-Mile
Site for use in establishing appropriate rates for
dumping of sewage sludge.
4.1*1.1 CTD Transect to the 106-Mile Site
During the southbound transit from Narragansett, Rhode Island to
the 106-Mile Site on March 1, 1988, a series of CTD profiles was made along a
line extending froi the edge of the continental shelf to the northern end of
the 106-Mile Site (Figure 4-1). The primary objectives of this CTD transect
were to (1) test all instrumentation prior to sludge plume surveying, and (2)
obtain information on the water column structure and characteristics in the
vicinity of the 106-Mile Site. Although only a small amount of time was
allocated for this transect survey, the data were useful for comparison with
the available maps of large-scale ocean thermal features as derived from
satellite thermal imagery.
A summary of the observed conditions along the CTD transect is
provided belowj Figures 4-2 and 4-3 illustrate the vertical and horizontal
characteristics of water properties along the transect.
* A surface layer of relatively cold (5-6°C), low salinity
(32.7-33.2 ppt) water of continental shelf origin
extended from the shelf to the northern portion of the
106-Mile Site. This observation was consistent with
regional interpretations of satellite thermal imagery
(see subsection 4.1.1.2).
* At the site, the layer of shelf water lay above normal
slope wat^ having maximum temperatures of «12°C and
maximum salinities of «35.3 ppt within a depth range of
100 to 175 m. (See temperature/salinity diagram in
Figure 4-2 for identification of water masses.)
• The thickness of the shelf water ranged from 75 m near
the edge of the shelf to 50 m at the northern end of the
106-Mile Site. This layer was significantly less dense
than the underlying slope water such that a strong
pycnocline was established at the boundary between these
two water masses.
4-2
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39'SO'N
31 30'H -
39 10'N -
38'80'N
71 10' N
ilOB-MllB Sita
71 0
71 40* «
Doptha in
FIGURE 4-1.
HAP SHOWING THE LOCATIONS OF THE R/V ENDEAVOR CTD PROFILE
STATIONS T-l, T-2, AND T-3, ALONG THE SOUTHBOUND TRANSECT ON
MARCH 1, 1988.
4-3
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25.5
0-
50-
100-
Jl 150-
200-
250-
300
0.3
13J
u
cc
a
11-
3-
7-
SS.Q
SIGMA-T
26.5 27.0
27,5
BEAM ATTENUATION (I/a)
O.i O.i 0.7 0.8
0.9
26.0
300
SAL1NITY (PPT)
32.5 33.0 33,5 34.0 34.3 . 3S.O 35.5 36.0
15-
Slope
Water
300m
Shelf
Hater
Surface
FIGURE 4-2. COMPOSITE OF HYDROGRAPHIC PROFILE RESULTS FROM STATIONS ALONG
THE SOUTHBOUND TRANSECT TO THE 106-MILE SITE: SIGMA-T PROFILES
(UPPER); BEAM ATTENUATION PROFILES (MIDDLE)j TEMPERATURE/
SALINITY CHARACTERISTICS (LOWER).
4-4
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TEMPERATURE ( C)
50 -
t
100 -
250 -
39'*0'
T.I
!
OXYGEN (mL/L)
T-3
50
-6.5 '
86-1
-6.5 -
S*
— 3.5 —
39 «0"
3B°20'
wrrnioe
38*10'
39'00'N
FIGURE 4-3. VERTICAL TRANSECT OF HYDROGRAPHIC PROPERTIES ALONG THE
SOUTHBOUND TRANSECT TO THE 106-MILE SITE: TEMPERATURE
SALINITY (MIDDLE); DISSOLVED OXYGEN (LOWER).
4-5
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Had the shelf water not extended to the 106-Mile Site,
the top of the main pycnocline might have been as deep as
150 to 200 m.
Dissolved oxygen concentrations were on the order of 7
ml/I in the surface layer of shelf water, whereas values
in the slope water (near 150 m depth) were as low as 3.2
mL/L because of biological consumption and considerable
time since surface ventilation.
Beam attenuation (natural turbidity) was highest («0.8
n-1) in the surface layer of shelf water; values were
generally «Q.5 nrl in the underlying slope water, except
for values in excess of 0.6 HT* within a deep layer at
the northern most station along the CTD transect.
4.1.1.2 Satellite Thermal Imagery
As indicated in a previous report ( EPA , 1988c), the Ocean
Frontal Analyses of the U.S. East Coast, prepared by the Marine
Climatological Investigation of the National Marine Fisheries Service in
Marragansett, Rhode Island, are useful for locating large-scale ocean thermal
features in the vicinity of the 106-Mile Site. These weekly, low-resolution
analyses provide a composite view of the Gulf Stream position, the location
of the shelf water/slope water front, and the positions of warm-core and
cold-core eddies formed by the Gulf Stream. These analyses are considerably
more useful during winter when there is a strong thermal contrast between the
water masses of different origin; in summer, solar warming of the surface
layer reduces the contrast between surface water masses.
Figure 4-4 presents a simplified version of the ocean frontal
analysis of February 29, 1988, the day before the southbound CTO transect to
the 106-Mile Site (see subsection 4.1.1.1). This map illustrates a surface
layer of continental shelf water extending well to the south of the
continental shelf and beyond the 106-Mile Site. This relatively cold (6 to
8°C) water mass had clearly displaced the warmer (12 to 13°C) slope water in
the vicinity of the site. Analysis of additional satellite images indicates
that this shelf water event persisted from roughly February 20 to March 20, a
period of 4 weeks. Over this time period, a Urge amount of sludge was
dumped at the 106-Mile Site and into this water mass. Although the surface
4-6
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profiles of current shear from the surface to 1300 m. The drifters were
primarily used (in conjunction with dye) to mark the specific portion of the
sludge plume that would be the focus of the individual plume survey.
Results from the two current measurement techniques are given in the
following subsections.
4.1.2.1 XCP Current Profile Results
Two expendable current profiler (XCP) probes were launched during
the survey (on March 2 and 3, 1988) to measure current shear in the upper
water column. As discussed in the final report for the nearfield monitoring
survey in September 1987 ( EPA , 1992c)( XCPs provide high-resolution
measurements of current shear, but they do not provide data on absolute
currents. Thus, the "relative" currents measured by the XCP differ from
absolute currents by an additive velocity factor that may vary with location
(due to the earth's magnetic field) and time (due to the strength of the
currents). For the 106-Mile Site, the magnitude of this adjustment should be
less than 10 cm/s, based upon discussions with the manufacturer.
The direct measurements of near-surface currents that were obtained
from the drifters during the March 1988 survey provide useful data for
comparison with the XCP results. As indicated in the following subsection,
the drifters at a depth of 5 m generally indicated northerly flow over the 3-
day survey period, whereas two drifters at 50 m moved toward the northwest
(to the left) of the surface currents. These results indicate that a 7 to 10
cm/s increase in the XCP1s north component of current speed is sufficient for
matching the absolute cm rents of the drifters and XCPs. After this
adjustment was made, analysis of the XCP profile data reveals the following
characteristics of the local current regime during the survey:
• Currents were northward at all levels, although there was
considerable shear in direction within the upper 100 m of the
water column due to the strong pycnocline.
Current speeds were less than «30 cm/s (0.6 kn) from the
nf
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Currents were strongest at the surface and within an
isothermal layer between 125 and 200 m which corresponded with
the slope water mass.
The surface layer of shelf water was moving northward in
association with northward flow throughout the water column
(to 1300 m). Hence, if sludge settled beneath the surface
mixed layer, its trajectory would still have been northward
during the time of the survey.
4.1.2.2 Near-Surface Drifter Results
Current profile data from the XCPs provided real-time information
during the plume-tracking operations, but deployment of near-surface drifters
proved helpful (1) as visual markers within the specific portion of the
sludge plume being tracked, and (2) for determination of currents 5 m below
the surface, where XCPs cannot provide good quality data on account of design
limitations.
Figure 4-5 presents a summary of drifter results from plume events
DB-IO and DB-11 (upper frame), and DB-13 and OB-14 (lower frame). Times and
positions are indicated for the launch and recovery of each drifter. In
addition to 5-m drogues for all four events, a single 50-m drogue was
deployed during plume events DB-10 and DB-14 for analysis of near-surface
current shear.
Analysis of the drifter results revealed that
* Near-surface currents were weak and relatively consistent over
the 3-day survey (March 2 to 4, 1988). Currents wire much
less intense than those observed during the nearfitld
monitoring survey in September 1987.
• Currents at 5 m were directed toward the north or northeast at
speeds of 0.6 kn or less.
* Currents at 50 m were directed toward the northwest (to the
left of the currents at 5 m) at speeds of roughly 0.2 kn.
The observed northward currents were in agreement with results froi
XCP current profilers. Both techniques suggest that the surface layer of
shelf water was migrating back toward the continental shelf, but additional
farfield current measurements would be needed to test this hypothesis.
4-10
-------
39 O'N
3fl*58'N
38 56'N
72* 6' W
OB-11
|t-2340
(5m)
t-2011
106-Mile Site
DB-10
t-1547 «L ^
(50m) ^» X
72 A' W
72' 2' K
t-lB38
(5m)
t-1212 _
72 0* W
38
38 48'N
38 45*N
72 S* M
DB-14
t-0849
(900)
yt-og
k / (So)
• t -0719
-0908
(5m)
t -2008
t-2254 ,
(5n.) ;
106-Mllo Site i
72 3*
72 1*
71*39' W
FIGURE 4-5. SUHMARY OF NEAR-SURFACE DRIFTER RESULTS FROM PLUME EVENTS DB-10
AND DB-11 (UPPER) AND DB-13 AND DB-14 (LOWER) DURINS THE MARCH
SURVEY AT THE 106-MILE SITE. TIMES ARE GIVEN FOR THE START AND
END POSITIONS OF EACH TRAJECTORY.
4-11
-------
4.2 BACKGROUND WATER QUALITY
Water collected at two stations located within the boundaries of
the 106-Mile Sludge Disposal Site was analyzed for contaminants for which
there are water quality criteria (Table 2-1), iron, total suspended solids,
C. perfringens. and selected trace metals in the particulate phase to provide
background water quality information at the site. Station BG-1, located in
the northeast corner of the site, was sampled at 5, 60, and 98 m for metals,
WQC parameters, and TSS just prior to sludge dumping in the same area.
Station BG-2, located near the center of the site, south of known dumping
activities, was sampled at 5 and 48 m for the same parameters. Samples for
analysis of organic compounds were obtained at a single depth at each
station, at 65 m at BG-1 and 16 m at BG-2. The hydrographic data from these
stations indicate that all the background samples, except for those obtained
at 98 m at BG-1, were collected in the layer of shelf water intruding over
the site during the survey. The sample from 98 m was located within the
permanent pycnocline.
Concentrations of metals in background water at the site were
generally 10 to 1000 times lower than the water quality criteria (Table 4-1).
Ambient concentrations of organic compounds were also low. Dieldrin and a
ClsPCB isomer were detected in one of the two duplicate samples from BG-1;
Endosulfan I and a ClyPCB isomer were found in one of two samples from BG-2.
No other organic compounds were detected. PCBs showed no distinct elution
pattern that could be matched to any commercial PCB formulation. No C.
perfringens spores were found in any of the 10 samples collected at these
stations. The TSS concentrations were low (0.32 to 0.80 mg/L). Contaminant
concentrations are compared to those found during the 1987 survey in Table
4-2.
Contaminant and TSS distribution in the background revealed several
results that may be related to the farfield fate of sludge dumped at the
si'te:
* TSS concentrations at the surface and at 98 m at station
BG-1 were 50 percent higher than those found at 60 m, and
were also 50 percent higher than those found at
4-12
-------
TABLE 4-1. BACKGROUND WATER QUALITY MEASUREMENTS IN SEAHATER AT THE
106-MILE SITE, MARCH 2-4, 1988.
Paraaeter
Metals
Arsenic, total
Cadmium
Chromium, total
Copper
Lead
Mercury
Nickel
Selenium
Silver
Zinc
Organic Compounds
Aldrin
Dieldrin
p,p'-DDT
p.p'-DDE
Endosulfan I
Endosulfan II
Endrin
Heptachlor
Total PCB
Total Suspended Solids
C. perfringens
Concentration
Range*
(»9/L)
0.93-1.52
0.018-0.024
0.13-0.15
0.19-6.41&
0.056-3. 9b
0.003-0.008
0.26-0.30
<.04
0.002-O.Q44G
0. 22-16. 1&
(ng/L)
NO
0.60
ND
ND
0.15
ND
NO
ND
ND- 0.25
(mg/L)
0.32 to Q.SQb
(1/100 iL)
0
EPA Marine
Hater Quality
Criteria
Chronic
2,319*
9.3
50*
2.9
5.6
0.025
8.3
54
_
86
_
1.9
1
-
8.7
2.3
3.6
30
-
Acute
43
1,100*
2.9
140
2.1
75
410
2.3
95
1,300
710
130
-
34
37
53
10,000
•
-
ND • Not Detected.
^Values for arsenic V and chromium VI are reported.
high value from 98 m with no confirming duplicate was obtained. Highest
concentrations without this sample were Cu, 1.68 0§/L; Pb» 3.8 ^g/L; Zn, 3.8
; and TSS 0.66 mg/L.
cThe extraction effeciency was only 50 percent; results are not corrected for
this efficiency.
^Highest values were in the particle maximum located in the pycnocline.
4-13
-------
TABLE 4-2. COMPARISON OF BACKGROUND HATER QUALITY MEASUREMENTS AT
THE 106-MILE SITE, SEPTEMBER 1987 and MARCH 1988.
Parameter
Metals (itg/L)
Arsenic, total
Cadmium
Chromium, total
Copper
Lead
Mercury
Nickel
Selenium
Silver
Zinc
September 1987*
0.93-1.29
0.013-0.024
0.11-0.15
0.17-0.23
0.033-0.12
0.004-0.013
0.23-0.27
<.03
0.002-0.020
0.02-0.20
Ranqe
March 19S8
0.93-1.52
0.018-0.024
0.13-0.15
O.li-S.41
0.056-3.9
0.003-0.008
0.26-0.30
<.04
0.002-0.044
0.22-16.1
Organic Compounds ng/L
Aldrin NO ND
Chlordane ND NA
Dieldrin ND ND-0.60
p.p'-DDT ND ND
p.p'-DDE ND ND
Endosulfan I ND ND-0,15
Endosulfan II NA NO
Endrin ND ND
Keptachlor NO ND
Total PCi ND-0.066 ND-0.25
«-BHC ND-9.4 NA
5-BHC ND-2.5 NA
Total Suspended Solids (mg/L)
0.16 to 0.93 0.32 to 0.80
C> perfrttiqens (1/100 «L)
NA » Not Analyzed,
ND * Not Detected.
a EPA (I992c).
4-14
-------
station BG-2. TSS concentrations at 60 m at BG-i and at 48 m
at B6-2 are similar and also similar to those found
at the site during the previous survey (Figure 4-6).
Copper and iron concentrations in surface waters were
higher at station BG-1 than at station BG-2, with copper
approaching water quality criteria at BG-1. Copper and
Iron concentrations at 60 w at BG-1 and at 48 m at BG-2
were lower than the surface, similar to each other, and
also similar to those found at the site during the
previous survey (Figure 4-6). Highest concentrations of
copper and iron were found at the pycnocline (98 m) at
station BG-1. Copper exceeded the water quality
criterion at this depth.
Lead and zinc, also analyzed in the same set of samples,
had similar distributions to those of copper and iron,
but concentration differences were not as pronounced as
those for copper and iron.
Other metals for which there are water quality criteria
(silver, arsenic, cadmium, chromium, nickel, selenium,
and mercury), analyzed only at 60 m at BG-1 and at 5 and
48 m at BG-2, had expected background concentrations and
expected relative concentrations (Table B-3, Appendix B).
Quality control information indicated that the elevated metals
concentrations were not the result of sampling artifacts or laboratory
contamination. Therefore, the data suggest some residual sludge fraction
resulting from previous dumping events may be present in the northern half of
the site-. Copper, iron, lead and zinc, being the most sensitive sludge
tracers, show the most noticeable concentration differences observed. Other
metal and organic contaminants, TSS, and C. perfringens did not reveal any
additional information regarding the potential contamination of the
background stations from sludge. The data from this survey were not
sufficient to determine whether the apparent background water contamination
is from a discrete plume remaining in the surface water or from an area-wide
increase in pollutant concentrations in the surface waters.
4.3 DUMPING INFORMATION
Barges vary greatly in terms of size, sludge capacity, dumping
method, maximum dumping rate, and method of propulsion (unpowered barges
4-15
-------
-------
versus self-powered tankers) ( EPA , 1992d). Most of the above factors
probably affect the initial, wake-induced dilution of sludge immediately
behind the barges, but a large number of nearfield surveys would be required
to quantify the effects of the various parameters. The results from the
nearfield survey in September 1987 illustrated that plume settling and
dispersion within the first 4 h after dumping was generally the same for the
four plumes surveyed, although the barges varied considerably in terms of
size, sludge volume, duiping method, and barge speed ( EPA , , 1992c).
These results suggested that barge configuration may have a smaller effect
upon initial sludge dilution than other factors such as dumping rate, sludge
characteristics, water column stratification, and oceanographic mixing
conditions.
To further investigate the degree to which barge characteristics have
a significant effect upon the nearfield behavior of sludge plumes, dumping
information was compiled for each of the sludge dumping operations surveyed
during the period of the survey from March 2 to 4, 1988. Table 4-3 presents
a summary of the barges for each of the six plume events (DB-10 through DB-
15), including barge dumping methods, sludge capacity of each barge, and the
origin of the sludge transported by each barge. Events DB-10 and DB-14 were
associated with sludge barges from the New York City Department of
Environmental Protection (NYCDEP)j both barges (Lemon Creek and Spring Creek)
carried sludge from the Wards Island facility. Dumping events DB-12 and DB-
13 were associated with barges carrying sludge from the Passaic Valley
Sewerage Commission. The sludge for events DB-11 and DB-15 originated at
Middlesex County and Nassau County, respectively.
With the exception of the small (180 ft), self-powered tanker OBI-IV.
the other barges ranged from 266 ft (Weeks 701) to 380 ft (NYCDEP barges) and
were towed to the site by tugs. Note that the sludge capacity of the OBI"
|V (200,000 gal") is roughly 18 times less than the capacity of a single
NYCDEP barge.
Table 4-4 presents information for the six dumping events listed in
Table 4-3. Sludge volumes, dumping times, and plume lengths were obtained
directly from the Ocean Dumping Notification Forms that are submitted to EPA
following each dumping operation. Average barge speed and average dumping
rates were calculated from the basic information of volume,
4-17
-------
TABLE 4-3. SUMMARY OF DUMPING METHODS, SLUDGE CAPACITY, AND ORIGIN OF
SLUDGE FOR EACH VESSEL DUMPING SLUDGE AT THE 106-MILE SITE
DURING THE PERIOD MARCH 2-4, 1988.
Survey
Vessel
Type
Diuoping Sludge Origin of
Method Capacity Sludge
(•illion gal)
DB-10
DB-11
DB-12
DB-13
DB-14
DB-15
Lemon Creek Barge Bottom Dump
LeoFrank Barge Bottom Dump
Weeks 701 Barge Bottom Dump
Morris Berrcan Barge Pump Out
Spring Creek Barge Bottom Dump
OB I-4
M/V
Pump Out
3.5 Wards Island
(NYC DEP)
1.3 Middlesex
County
1.5 Passaic
Valley
2.8 Passaic
Valley
3.5 Wards Island
(NYC DEP)
0.2 Nassau County
4-18
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TABLE 4-4. SUMMARY OF DUMPING INFORMATION FOR BARGES DUMPING SLUDSE AT THE 106-MILE SITE
DURING THE PERIOD MARCH 2-4, 1988.
Survey
Date
Tug
Barge
Sludge
Volume (gal)a
Barge
Speed (kn)b
Dumping
f Time (h)a
M3
Plume
Length (nnti)a
Volume
Dumping
Rate (gal/min)b
Effective
Dumping
Rate (gal/ft)b
DB-10
3/2
Sheila Moran
Lemon Creek
3,366,225
5.2
4.0
21.0
14,026
26.4
DB-11
3/2
Emily S
Leo Frank
1,290,114
7.3
1.5
11.0
14,335
19.3
DB-12
3/3
Elizabeth
Weeks 701
1,424,340
10.5
0.6
(0.2)d
6.3
40,695
(118,695}d
37.2
(137. 9)d
DB-13
3/3
Kate
Morris Berman
2,928,206
7,3
3.8
27.8
12,843
17.3
DB-14
3/4
Esther Moran
Spring Creek
3,515,835
4.6
4.0
18.5
14,649
31.3
DB-15
3/4
_
OBI-4
200,000
3.9
1.7
6.6
1,961
5.0
provided on Ocean Dumping Notification Forms.
^Calculated from data provided on Oceen Dumping Notification Forms.
cEstimates based upon observations from survey vessel and aerial reconnaissance.
^Calculated from barge speed of 10.5 kn and plume length of 1.7 nmi.
-------
dumping time, and plume length. Sludge volumes for the individual barges
ranged from 200,000 to roughly 3.5 million gallons: barge speeds varied from
3.9 to 10.5 kn. With the exception of the Keeks 701. dumping times ranged
from 1.5 to 4 h; the tfeeks 701 dumped its entire load of sludge in 0.6 h.
Average volume dumping rates (in gal/min) have been determined from
the sludge volume divided by the dumping time. For the NVCDEP barges (Lemon
Creek and Spring Creek), the Leo Frank, and the Morris Berman, volume dumping
rates were between 12,800 and 14,700 gal/min, less than the maximum court-
ordered rate of 15,500 gal/min. The OBI-4. a vessel which pumps sludge from
its holding tanks, has a maximum pumping rate of approximately 2,000 gal/min
as indicated in Table 4-4. Figure 4-7 illustrates the variations in volume
dumping rates and barge speeds for each of the dumping events surveyed.
The average volume dumping rate of the Weeks 701. 40,695 gal/min, was
nearly 3 times the court-ordered rate of 15,500 gal/min, as determined from
the volume of the sludge and the dumping time provided on the Ocean Dumping
Notification Form. Measurements of this sludge plume during the nearfield
survey (event DB-12) revealed, however, that both the position and the length
of this plume were different from those noted on the Ocean Dumping
Notification Form. The direct measurements of the plume exhibited an
extremely wide and concentrated plume that was roughly 1.7 nmi long; with a
barge speed of 10.5 kn, this would result in a dumping time of 0.2 h and a
volume dumping rate of nearly 120,000 gal/min.
The survey of barge characteristics ( EPA , 1992d) revealed that
the Weeks 701 and Weeks 702 could dump their entire load in 30 minutes or
less, such that dumping rates would reach 140,000 gal/min. The exact rate at
which the Weeks 701 dumped its load on March 3, 1988, cannot be determined
from the available 'nformation, but the above evidence suggests that the
rate was 3 to 8 times the court-ordered rate of 15,500 gal/min. The
characteristics of this plume, which are presented in subsection 4.4, support
the presumption of high dumping rate for the Keeks 701.
Estimates of the effective dumping rate, expressed in units of
gallons per foot of plume length, for each of the six dumping events are
given in Table 4-4; the relationship between volume dumping rates and
effective dumping rates is demonstrated in Figure 4-7. It has been shown
4-20
-------
( EPA , 1992d) that the effective dumping rate (in gal/ft) has a greater
effect upon the nearfield behavior of sludge plumes than the volute dumping
rate, expressed in units of gallons per minute. With a maximum court-ordered
volume dumping rate of 15,500 gal/rain and a minimum allowable barge speed of
3 kn, the implied maximum effective dumping rate is 51 gal/ft. As indicated
in Table 4-4, the two NYCDEP barges (events DB-10 and DB-14), the Leo Frank
(DB-11), and the Horn's Berman (DB-13) had effective dumping rates between 17
and 32 gal/ftj the OBI-IV had a low rate of 5.0 gal/ft on account of its slow
pumping rate.
In contrast to the other dumping events, the Weeks 701 (event DB-12)
had a high effective dumping rate (between 37 and 138 gal/ft) in spite of its
high barge speed (10.5 kn). Direct observations of the plume from the Weeks
701 (see subsection 4.4) support the assumption that the effective dumping
rate for this barge event (w!38 gal/ft) may have been 8 times the rate of the
Morris Berman («17 gal/ft) and 28 times the rate of the QBI-IV (5 gal/ft).
This analysis of dumping rates suggests that the three categories of
sludge plumes were surveyed during the March 1988 survey at the 106-Mile
Site:
* A highly concentrated plume from the Weeks 701 with an effective
dumping rate of over 100 gal/ft
* Moderate plumes from the NYCDEP barges, the Leo Frank, and the
Morris Berman. with effective dumping rates of 17 to32 gal/ft
• A weak plume from the OBI-IV with an effective dumping rate of 5
gal/ft.
4.4 SLUDGE PLUHE BEHAVIOR
4.4.1 Vertical and Horizontal Spreading
To determine the short-term mixing and dispersion characteristics of
sludge plumes that were dumped at the 106-Mile Site during the survey, it is
first necessary to quantify their spatial scales and the rates at which they
vary. The following sections present analyses of sludge plume thickness and
4-22
-------
width, as determined from (1) the shipboard profiling with the
CTD/transmissometer system, and (2) aerial photography.
4.4.I.J Vertical Spreading
Vertical profile measurements within the individual sludge plumes
were effective for determining the short-term vertical distribution of sludge
throughout the upper water column. As demonstrated during the nearfield
monitoring survey in September 1987, the optimum parameter for monitoring
vertical plume behavior was in situ turbidity, as measured by the beam
transmissometer mounted on the CTO sensor package. Due to the high total
suspended solids (TSS) content of the sludges, it was possible to detect
sludge at very high dilutions and for many hours after dumping.
Table 4-5 illustrates the range of TSS concentrations for the sludges
surveyed during this survey and compares them to those of the previous
(September 1987) survey at the 106-Mile Site. For each plume event (DB-1
through OB-4 for the September survey, and DB-10 through DB-15 for the March
survey), the origin of the sludge and the mean TSS concentration of the
sludge, as estimated by Santoro and Fikslin (1987), are indicated. The mean
TSS concentration of the sludge from Passaic Valley, 79,965 mg/L, is clearly
much greater than the TSS concentration of the other sludges (roughly twice
that of the Middlesex County sludge and 4 times that of Wards Island and
Nassau County sludges). As expected, sludge from Passaic Valley was
considerably easier to track with the in situ transmissometer than sludge
from other facilities.
The results from the individual turbidity profiles were most useful
for analyses of plume thickness and identification of maximum sludge
concentrations within the water column. Plume thickness, defined as the
maximum observed depth of sludge penetration, provides a measure of short-
term settling of sludge. Figure 4-8 presents a composite time series of
observed plume thickness for sludge plumes surveyed in this survey and
compares the data to the previous surveys.
The previous survey produced the following conclusions about vertical
dispersion under summer oceanographic conditions:
4-23
-------
TABLE 4-5. SUMMARY OF TOTAL SUSPENDED SOLIDS CHARACTERISTICS FOR THE
SLUDGES SURVEYED DURING THE SEPTEMBER 1987 AND MARCH 1988
SURVEYS AT THE 106-MILE SITE. TSS ESTIMATES FROM SANTORO AND
FIKSLIN (1987).
PI UK
Event
DB-1
DB-2
DB-3
DB-4
DB-10
DB-11
DB-1 2
DB-13
DB-14
DB-15
Survey
Date
1/87
H
H
II
3/88
u
H
O
II
II
Treatment
Facility
Wards Island (NYCDEP)
Wards Island (NYCDEP)
Port Richmond (NYCOEP)
26th Ward
Wards Island (NYCDEP)
Middlesex County
Passaic Valley
Passaic Valley
Wards Island (NYCOEP)
Nassau County
Mean TSS
(•g/D
18,067
18,067
26,471
25,217
18,067
33,496
79,965
79,965
18,067
17,462
4-24
-------
i
ro
tn
x-s
to
CO
UJ
§
o
3:
h-
UJ
_J
n
O-i
10-
20-
30-
40-
50-
60-
70-
80-
90-
ft— YD % — -m • , D n
• ,
•
\ September 198? March 1988 Vessel
\
\ ODB-3 ADB-12 Weeks 701
\ ODB-1 •DB-13 Morris Bernan
K • DB-14 Spring Creek
- ' TDB-15 OBI-4
\
•x.
~~ ~~ — A- _ _„,„, .
-'— A
r i I 1 -— -
-""I I 1 '
0 12 3 4 £
TIME (hours)
FIGURE 4-8. TIME SERIES PLOT OF PLUME THICKNESS FOR PLUMES SURVEYED IN
SEPTEMBER 1987 (OPEN SYMBOLS) AND MARCH 1988 (SOLID SYMBOLS).
-------
• Initial (0 to 5 min) mixing within the wake of the barge
resulted in sludge penetration to 10 to 15 m, the approximate
draft of the barges.
• Vertical mixing processes resulted in sludge penetration to
roughly 18 m four hours after dumping. This depth corresponded
with the top of the seasonal pycnocline.
« There was no indication that sludge settled to depths greater
than 20 m, with penetration beneath the seasonal pycnocline.
* The results from four plume surveys in summer were similar,
although four different barges and three different sludge types
were surveyed.
The profile results from this survey, which are indicated by solid
symbols in Figure 4-8, illustrate many of the settling (thickness)
characteristics similar to those observed during the previous survey. The
majority of the plume thickness measurements during the first 2 h of plume
events DB-13, OB-14, and DB-15 exhibited values ranging from 15 to 25 m, in
agreement with the summer results. Plumes from the Spring Creek and the
Morris Bennan were surveyed during both seasons,* the Spring Creek carried
sludge from Wards Island both times, and the Morris Berman carried sludge
from Port Richmond (September) and Passaic Valley (March).
The 35-m thickness observed 1.2 h after dumping for plume event DB-13
most likely represents the settling of a heavy fraction of Passaic Valley
sludge on the axis of the plume. The horizontal, cross-axis scale of this
segment of the plume must have been 10 m or less, and/or this feature must
have been short-lived because this structure was not sampled again over the
next 2 h. Nevertheless, this observation illustrates that, during the winter
survey, a fraction of the sludge from plume event DB-13 penetrated bt.ow the
20 m level that was observed for summer plumes.
The most striking difference between the summer and winter plume
thickness results presented in Figure 4-8 was the deep penetration of Passaic
Valley sludge from the Weeks 701 during plume event DB-12. Although the
nearfield measurements did not begin until well after sludge dumping, the
direct observations revealed plume thicknesses of roughly 80 m between 2.7
and 4 h after dumping. These thicknesses were (1) greater than all other
plume observations during both the winter and summer surveys, and (2) greater
than the mixed-layer depth, such that sludge had clearly penetrated the upper
4-26
-------
boundary of the pycnocline which was situated at 50 m. Thus, Passaic Valley
sludge dumped during plume event DB-12 settled much deeper than Passaic
Valley sludge dumped during plume event D8-13. It is believed that the deep
penetration of plume DB-12 was due to the extremely high dumping rate (40,000
to 118,000 gal/min) of the Weeks 701. as discussed in subsection 4.3. This
enhanced settling may be caused by increased flocculation when sludge is
dumped rapidly and initial dilutions are low (Lavalle et al., 1988).
To summarize, the winter observations of plume thickness have
demonstrated the following short-term (0 to 4 h) characteristics of sludge
plumes:
• Plumes generally remained within the upper 25 m of the water
column during summer and winter provided that dumping rates were
15,500 gal/min or less.
• Winter plumes did not reach the base of the mixed layer (50 to
150 m) except when dumping rates were much greater than 15,500
gal/min.
* Plume thickness was highly dependent upon dumping rate; sludge
has been observed to penetrate the pycnocline within the first
3 h after dumping when sludge is dumped faster than the court-
ordered rate of 15,500 gal/min.
* Barge configuration, dumping method, sludge characteristics, and
seasonal variations in water column stratification all had a
smaller effect upon sludge settling than the dumping rate.
4.4.1.2 Horizontal Spreading
Plume width Hata were obtained for plume events DB-10, DB-11, and DB-
12 during the survey. These estimates of plume width were determined from
(1) horizontal profiles of turbidity using the shipboard profiling with the
CTD/transmissometer system, and (2) aerial photographs of the surface
turbidity boundaries of the plume. These analyses were conducted in the same
manner as the analyses of plume width from the September 198? survey data
( EPA , 1.992d).
For plume event DB-10, analysis of aerial photographs provided
accurate estimates of plume width during the first 16 min following dumping.
As indicated in Figure 4-9, plume widths increased from 29 to 163 m during
4-27
-------
this period following dumping. As observed during the summer (Septeiber
1987} survey, the rate of horizontal spreading was greatest during the first
few minutes when mixing was active due to turbulence in the wake of the
barge.
Plume width estimates from roughly 1 to 3 h following dumping for
plume event DB-10 were obtained from the horizontal profiles of
transmissometry data. As indicated in Figure 4-9, plume widths increased
from roughly 240 to 700 i» during this time period. Both the magnitude and
the rate of spreading for plume event DB-10 were similar to the observations
during September 1987; the plumes in the summer exhibited widths between 175
and 350 in one hour after dumping.
During plume event DB-11, which began at 2011 hours on March 2, 1988,
a total of 18 horizontal tows were conducted during darkness. From real-
time, on-board analysis of the profile results, it was determined that the
dumping rate varied significantly along the barge track, and that the dumping
rate must have been significantly (5 to 10 times) less than 15,500 gal/min
rate at the location of the initial (time 0) profiling transects. After low
turbidity values had been observed during the first few plume transects, the
survey plan was modified in order to acquire profile data from another
location along the plume. Because the horizontal profile data from plume
event DB-11 did not provide a useful 2 to 3 h time series of plume width from
a single location within the plume, the results from event DB-11 are not
shown in Figure 4-9.
Plurae width estimates are also lacking for the first 2 h following
dumping for plume event DB-12 because the Heeks 701 had dumped its load
before the survey vessel had reached the position of the barge (outside of
the site). Plume width oata from event DB-12, acquired by the in situ
transmissometer system, are presented in Figure 4-9. These data illustrate
that plume widths increased from roughly 500 to 1200 m during the period from
2 to 4 h following dumping. The results are quite similar to those from
plume event DB-10, which is surprising because the rate of dumping for plume
event DB-12 (40,000 to 118,000 gal/min) was much greater than the dumping
rate for plume event DB-10 («14,000 gal/min).
To summarize, the winter observations of plume width demonstrated the
following short-term (0 to 4 h) characteristics of sludge plumes:
4-28
-------
1600
1200--
3"
I—
Q
^
LJ
^
r>
_j
D_
800
WINTER SURVEY
MARCH 1988
400
DB-10
0
60
120
180
240
TIME (h)
FIGURE 4-9.
TIME SERIES PLOT OF PLUME WIDTH FOR PLUHE EVENTS OB-IO AND DB-
12 SURVEYED IN MARCH 1988. DATA HERE DERIVED FROM AERIAL
PHOTOGRAPHY AND IN SITU PROFILE MEASUREMENTS.
-------
Plume widths and the rate of horizontal spreading during winter
were similar to those observed during the summer (September
1987) survey. However, wind and wave conditions during the
winter survey were so mild that the winter mixing conditions
were not unlike those observed during summer; near-surface
current shear was also much less intense during the winter
survey.
Plume widths did not vary according to barge configuration,
dumping method, sludge characteristics, or water column
stratification; surface nixing conditions (winds and waves) and
sludge dumping rates are expected to have the most significant
effect upon horizontal spreading rates.
Horizontal spreading rates were greatest (30 to 40 cm/s) during
the first few minutes after dumping due to turbulent mixing
within the wake of the barge; between 1 and 4 h after dumping,
spreading rates were 5 to 10 cm/s.
However, these survey results did not represent active winter mixing
conditions (high winds and waves) that would result in greater rates of plume
spreading and dilution. In addition, neither the summer (September 1987)
nor the winter (March 1988) survey was conducted when a warm-core Gulf Stream
eddy was present at the site. During such periods, currents are much
stronger and the rate of plume dilution may consequently be much greater than
demonstrated by the two recent nearfield surveys.
4.4.2 Sludge Dilution and Transport
Analyses of the sludge plume measurements made during the survey
revealed that sludge plumes generally have a core of relatively concentrated
sludge, at least during the first 4 to 8 h after dumping. Because of the
oceanographic mixing processes (e.g., winds, waves, and current shear) that
cause plume advection and dispersion, this core was not always situated at
mid-depth within the plume, nor along the linear axis of tha plume.
Likewise, the frequency distribution of sludge concentrations within the
plume was far from Gaussian.
Although the behavior of the relatively concentrated core of the
plumes was difficult to monitor, let alone predict, it is this core that is
4-30
-------
of greatest concern to EPA because ocean dumping regulations specify that
concentrations of contaminants in parcels of ocean-dumped sludge may not
exceed water quality criteria 4 h after dumping, or at any time outside of
the designated site. Estimates of plume-averaged dilution! based upon known
dumping rates and direct measurements of plume width and thickness, are
inappropriate for testing compliance with water quality criteria because
they overestimate sludge dilution within the core of the plumes.
The results from the survey illustrated that plume-averaged
dilutions were much greater than dilutions of concentrated parcels of sludge
within the core of plumes; the ratio of plume-averaged dilution to parcel
dilution at 0, 1 and 2 h after dumping was approximately 2.5, 10 and 33,
respectively. Figure 4-10 illustrates this difference between plume-averaged
dilution and parcel dilution for plume event DB-3 surveyed in September 1987.
The parcel dilutions were derived from trace metal analyses of water samples
collected within the concentrated core of the plume ( EPA , 1992c).
Based upon the need to determine the rate of sludge dilution within
the core of the plumes, this section presents analyses of dilution within the
sludge plumes monitored during the nearfield survey in March 1988 and
compares the results to those of the previous survey. Subsection 4.4.2.1
presents an analysis of dilution based upon vertical and horizontal profiles
of turbidity acquired using the in situ profiling system. Subsection 4.4.2.2
presents results of analyses of dilution based upon trace metal
concentrations from discrete water samples collected within the plumes.
These results are followed by a discussion of the horizontal transport of
sludge plumes monitored during the survey (section 4.4.2.3).
4.4.2.1 Dilution Based on Transmissometry Data
Analyses of the transmissometry data focused on determination of the
rate of dilution within the core of the plumes. Two steps were required to
achieve this objective:
1» Identification of the most concentrated portion of the plume on
each vertical profile and horizontal tow.
4-31
-------
100,000
10.000
Q
Q
UJ
PLUME
AVERAGE
Ui
IS3
ui
o
1.000
DISCRETE
PARCELS
TRACE METALS
100
PLUME EVENT DB-3
SEPTEMBER 1987
1 1 1 J 1
/•*. . /> f*
uu o o
r»i_ A A
KD " "
7 M-, n ± i o
zn u u
1 1 1
4 5
TIME (hours)
8
FIGURE 4-10.
TIKE HISTORY OF SLUDGE DILUTION FOR PLUME EVENT DB-3 DURING
SEPTEMBER 1987. SOLID SYMBOLS REPRESENT AVERAGE DILUTION OF
ENTIRE PLUME; OPEN SYMBOLS REPRESENT TRACE METALS RESULTS FROM
DISCRETE HATER PARCaS WITHIN THE CORE OF THE PLUME.
-------
2. Estimation of dilution as a function of time for the most
concentrated portion of the plume.
The results from these individual steps are presented below. The
only major assumption inherent in these analyses is that a subset of the
transraissometry profiles (either vertical or horizontal) from each plume
event intersected the most concentrated portion of the plume. These "core"
profiles were easily identifiable dut to the high concentrations of
turbidity (beam attenuation) relative to background levels.
Identification of the Plume Core
Although turbidity readings were obtained at 30-cm vertical intervals
within tha plumes during vertical profiling, the highest value of turbidity
did not provide a statistical representation of the sludge concentrations
within the core of a plume. To better resolve the distribution of sludge
(turbidity) concentrations, vertical and horizontal profiles of beam
attenuation were analyzed to obtain the percent frequency of occurrence of
beam attenuation within specific bins of beam attenuation that range from
the highest concentration within the plume to the relatively low values found
in the receiving water. After each profile was edited to retain only those
measurements from within the plume, the objective sorting analysis yielded
results that were independent of (1) the location of the plume within the
water column, (2) the vertical and horizontal scales of the plume, and
(3) the sampling resolution and direction (vertical or horizontal) of the
profile.
Figure 4-11 presents a composite of concentration distributions fo,-
four vertical profiles acquired during plume event DB-13 in March 1988. For
each profile, the percent frequency of occurrence of 1-s beam attenuation
values is indicated for the range of beam attenuation values observed. For
profile 3 made 0.33 h after dumping, the maximum beam attenuation exceeded
34 m-i, and the most common reading was 26.8 m~l. For the subsequent
profiles during this.2-h sampling period, there was a clear progression
toward lower beam attenuation values versus time since dumping. The maximum
beam attenuation value for profile 16, which was made 2 h after dumping, was
19 m-1, and the most common value was 1.4 m-1. The relatively high percent
4-33
-------
0 -|i—!£-
10 IS 20 2S
BEAM ATTENUATION |.-'|
20
M-l)
PROFILE 6
TIME =• 0.73h
10 15 20 25
BEAM ATTENUATION (••')
Ul
CL
10
10
PROFILE 15
TIME = 1.75h
1—
15 20 23
BEAM ATTENUATION I--1)
30
PROFILE J6
TIME » 2.Oh
10
-f-
15
20
BEAM ATTENUATION (•->)
30
35
FIGURE 4-11.
COMPOSITE OF TURBIDITY (BEAN ATTENUATION) ANALYSES FOR
INDIVIDUAL VERTICAL PROFILES OF PLUME EVENT DB-13 IN MARCH
1988. DATA ILLUSTRATE PERCENT FREQUENCY OF OCCURRENCE WITHIN
BINS OF BEAM ATTENUATION.
-------
of occurrence (26%) of low turbidity readings illustrates that the plume had
not only become more dilute, but had become more homogenized.
For comparison with the results from plume event DB-13 acquired
during the survey, Figure 4-12 presents a similar analysis of beam
attenuation values within plume DB-3 surveyed in September 1987. Both
surveys included vertical profiling within plumes dumped by the Morris
Berman; however, the origin of the sludge differed for the two events as
discussed in Section 4.3. The results from the two surveys are quite
similar: maximum beam attenuations decreased, the value of the most common
beam attenuation reading decreased, and plumes became more homogenized with
time after dumping. This short-term behavior of sludge plumes was also
determined from similar analyses of horizontal profile data from other plumes
surveyed during September 1987 and March 1988.
Parcel analysis for each profile (either vertical or horizontal) was
also used to quantify, on a volumetric basis, the concentration of the most
concentrated portion of a plume. The plume core was defined by a 10 percent
threshold (above which 10 percent of the plume measurements lay). This value
was chosen arbitrarily, but it may be a reasonable and objective criterion
for characterization of the densest part of a plume. The temporal behavior
of this plume core was compared with the maximum and median beam attenuation
values of the profile.
Figure 4-13 presents time series plots of (1) the 10-percent value
(plume core), and (2) the median value of beam attenuation as derived from
the analyses of individual profiles described above. In the upper frame,
results from plume event DB-13 of March 1988 are presented versus time for
the first 2 h following dumping. This figure illustrates that both the plume
core and the median value of beam attenuation decreased sharply during this
time period. The fact that the plume core results were less consistent
(linear) than the median results is most likely related to the difficulty in
sampling the densest part of the plume using vertical profiling techniques.
The middle frame in Figure 4-13 presents the results from plume event
DB-3 of September 1987. This figure illustrates that shortly after dumping,
both the plume core value and the median value of beam attenuation were near
5.1 m~l. With increased time after dumping, both values decreased but the
instantaneous difference between the two quantities was much less than that
4-35
-------
t- 30--
UJ
O
K
ui
O. 20
W-l
234
BEAM ATTENUATION (•->)
so
H. JO- •
u
O
s
a. 20--
10
0*-1
PROFILE 4
Tint - 0,22 h
..CK*-
BEAM ATTENUATION (»-')
I
U)
-------
25--
i »| \
s 1 s-
\ 10*
\
-
Z
UEOUH \
\
\
-t-
2
TIME (h)
TIME (h)
5-.
\
7 * V ID*
§ \ ^
6 , L \ \
DB - 13
WINTER
OB - 4
SUMMER
M ATTENIW
M I
fl
m ,.
ft .
> "v-
UEDMH \ •
\ V
^^~~ ~~~—
•• — 1
TIME (h)
FIGURE 4-13.
COMPOSITE OF TURBIDITY (BEAM ATTENUATION) ANALYSES WITHIN THE
CORE OF THE PLUME FOR EVENTS DB-13 (UPPER), DB-4 (HIDDLE), AND
DB-4 (LOWER). DATA ARE PRESENTED FOR THE MEDIAN TURBIDITY AND
THE VALUE REPRESENTING THE MOST CONCENTRATED 10% OF THE PLUME.
4-37
-------
observed during plume event DB-13 in Harch 1988. The Mgher variability of
beam attenuation values within the core of plume DB-T3 may have been due to
the high turbidity of the Passaic Valley sludge («15 w-1 at 1 h) compared to
the relatively low turbidity of the Port Richmond sludge («4 nrl at 1 h) from
plume DB-3.
The lower frame of Figure 4-13 presents the results from plume event
DB-4 of September 1987. This figure illustrates that both the plume core
value and the median value of beam attenuation within plume DB-4 decreased
rapidly during the first 2 h after dumping; from 2 h the rate of decrease
(dilution) was less.
Plume DB-4 was surveyed using horizontal profiling, whereas plumes
events DB-3 and DB-13 were surveyed using vertical profiling. From the
results of plume DB-4, it appeared that horizontal profiling may be the best
technique for monitoring the short-term behavior of sludge-plume cores. For
instance, the lower frame of Figure 4-13 illustrates a gradual, monotonic
progression to lower values of beam attenuation for both the plume core value
and the median value of the plume. During the first hour after dumping,
median values decrease more rapidly than the plume core values, suggesting
that the core of the plume was being diluted more slowly than the average for
the entire plume. Beyond 1 h, the densest part of the plume was diluted more
rapidly than the average plume such that at 3 h, the plume was nearly
homogeneous and the concentrated core was practically gone.
Estimation of Dilution within the Plume Core
The previous discussion presented a method for quantifying the
turbidity characteristics and temporal behavior of the most concentrated
parcels of sludge within sludge plumes monitored at the 106-Mile Site.
Hence, this analysis of turbidity data within the core of the plumes is
analogous to analyses of TSS and trace metals data from discrete water
samples within the core of the plume. As illustrated in Figure 4-10, the
trace metal data from plume DB-3 in September 1987 indicated that, after the
initial (5 min) period of wake-induced mixing, the rate of dilution within
the core of the plume was roughly 1,000:1 per hour for the first 4 h after
dumping. Although there were uncertainties in the concentrations of metals
4-38
-------
within the undiluted sludge from this and other barges surveyed in September,
the results from the individual plume events suggest that a dilution rate of
1,000:1 per hour may be representative of short-term sludge plume behavior
during summer months.
Using (1) the results of the turbidity analyses for the September
1987 and March 1988 plume surveys (Figure 4-13), (2) transmissometer
calibration information for conversion from beam attenuation readings to
total suspended solids (TSS) concentrations, and (3) estimates of the TSS
concentration of the individual (pure) sludges from Santoro and Fikslin
(1987), rates of dilution for the core of the plumes can be determined from
the transmissometry data. Table 4-6 presents rate-of -dilution estimates for
plumes DB-13 (this survey) and DB-3 and DB-4 (previous summer); rates are
given for the plume core (most concentrated 10% by volume) and the plume
average (based upon median turbidity values). The results from the plume
core indicate that rates of dilution during the first 2 h following dumping
were between 2,500:1 and 5,OOOU per hour, which are quite similar to the
rate of dilution (1,000;1 per hour) that was determined from the results of
trace metal analyses within plume DB-3. Rates of dilution within the core
of the plumes became higher as time from T=0 h increased (e.g., 28,735:1 per
hour for plume DB-4 from 1.5 to 3.0 h after dumping). Rates of dilution were
also much higher for analyses based upon the median TSS concentration within
the plumes, rather than concentrations within the core. This analysis
indicated that
• Transmissometry data from the core of plumes can be used to
estimate rates of dilution; the results are in agreement with
results from analyses of trace metals concentrations within
water
During the first 2 h after dumping, the core of a plume dilutes
at a rate that is significantly less than the rate for the
average plume.
The rate of dilution within the core of a plume increased with
time after dumping; this is presumably a result of erosion
(dilution) of the plume from its outer boundaries and a
reduction in volume of the core.
4-39
-------
TABLE 4-6. SUMMARY OF PLUME DILUTION RATES BASED UPOK TRAHSMISSOMETRY
DATA FROM PROFILING SURVEYS IN MARCH 1988 (DB-13) AND
SEPTEMBER 198? (DB-3 AND DB-4).
Rate of Dilution (per hour)
Tine After Upper 10%
Plume Event Date Dumping (h) (piuse core) Median
DB-13 3/88 0.5-2.0 2,850s! 11,520:1
DB-3 9/87 0.0-3.0 2,600:1 3,790:1
D8-4 9/87 0.0-1.5 4,780:1 20,440:1
1.5-3.0 28,735:1 191,870:1
4-40
-------
Analyses of dilution rates from transmissometry data would be greatly
improved with (1) accurate measurements of TSS concentrations within the
sludges surveyed and (2) laboratory calibration of the transmissometers using
samples of the various sludges.
4.4.2.2 Estimation of Dilution Based on Chemical Tracer Data
Data on metals from sludge plumes surveyed were compared to sludge
contaminant data to calculate sludge dilution at the site. The summer 1987
survey showed that sludge dilution consisted of an initial turbulent dilution
occurring in the barge wake, and a slower continuing dilution resulting from
settling and dispersive oceanic processes ( EPA , 1992c), The data from
this survey were not as extensive as those from the previous survey, but
generally showed the same pattern of sludge dilution.
Dilution estimates calculated from sludge tracers require information
on the initial concentrations of tracers in sludge. However, because sludge
was not collected from barges dumping at the site, historical sludge
contaminant data (Santoro and Fikslin, 1987) were used for calculation of
dilution. Use of this historical contaminant data introduces an unknown
level of uncertainty in the calculated dilution estimates because actual
contaminant levels in the sludges studied probably differ from average
historical levels. However, without a historical sludge contaminant data
set, dilution calculations could not be made for this survey.
Although data on metals from five plumes were obtained, initial
turbulent dilution could only be calculated for two of the plumes because of
uncertainties in the sludges contained in two of the barges. The NYCDEP
facility at Wards Island combines sludges from several plants in barges for
disposal at sea. Because the plants contributing to the two barges
originating from Wards Island could not be identified, historical data could
not be assigned with any confidence. Therefore, sludge dilution from dumping
events DB-10 and DB-14 could not be determined. Tracer samples from DB-11
were clearly not collected in the particle maximum (core) of the plume, and
dilution calculations were not made from this plume.
For those plumes with identified sludge sources, of initial sludge
dilution was estimated from chemical tracer data (Table 4-7). Estimates
4-41
-------
TABLE 4-7. ESTIMATES OF INITIAL DILUTION FOR SEWAGE SLUDGE PLUMES STUDIED
IN MARCH 1988. RESULTS BASED ON OBSERVED METAL CONCENTRATIONS
IN THE PLUME AT T=0 h AND DATA FROM SANTORO AND FIKSLIN
(1987).
Concentration
Plume
DB-10a
DB-11&
DB-12C
DB-13d
DB-14a
DB-15
POTW
Wards
Island
Middlesex
County
Passaic
Valley
Passaic
Valley
Wards
Island
Nassau
County
Metal
Cu
Pb
Zn
Cu
Pb
Zn
__
Cu
Pb
Zn
Cu
Pb
Zn
Cu
Pb
Zn
Sludge
(«g/U
NA
NA
NA
128
64
352
__
115
318
137
NA
NA
NA
7.4
2.4
12.1
T=0 h
(M9/L)
19.5
14.1
17.2
0.40
0.40
1.5
__
7.5
34.5
35.7
12.4
9.7
28.8
4.9
2.1
6.4
Sludge Plume
Initial
Dilution
--
—
__
--
--
__
15,300:1
9,200:1
3,800:1
_ v
__
--
1,500:1
1,140:1
1,890:1
aOrigin of sludge unknown. Cannot calculate initial dilution.
^Samples were not collected from the particle maximum in the plume;
dilution estimates not feasible.
cplume not sampled for tracer parameters.
^Initial samples at T=0.3 h were not collected from the plume core.
4-42
-------
range from an initial 1,140:1 dilution for DB-15 to a 15,300:1 dilution for
DB-13. Estimated dilutions for individual plumes varied according to metal,
most likely indicating that actual sludge contaminant concentrations
differed from historical data. Generally, the range of estimated initial
dilution calculated from the March 1988 data was similar to that calculated
from the September 1987 data.
Table 4-8 presents estimates of continuing short-term dilution (after
initial turbulent dilution), and estimates of overall rate of sludge dilution
with time. Calculations of overall sludge dilution agree with results found
in September 1987, and indicated that relatively little additional short-term
sludge dilution (less than 10-fold dilution per hour) occurred at the site
after initial barge-induced dilution.
The overall dilution calculated for DB-13 from chemical tracer data
ranged from 5,500tl to 14,400:1 per h, depending on the metal used to
calculate dilution. These dilution rates were up to 5 times those
calculated from light transmission data in the plume core (Table 4-6), but
were similar to median dilutions calculated from the same light transmission
data. This comparison provided an excellent check on the data. The
difference in the two calculations indicates that (1) samples for chemical
tracer analysis were not collected in the plume core, (2) historical sludge
contaminant data did not reflect actual sludge levels, or (3) partitioning of
contaminants from particles to dissolved phase (Section 4.6) may have
resulted in higher contaminant levels than was reflected in the particulate
loading.
Calculations of sludge dilution from chemical tracer data provide
estimates of initial and continuing sludge dilution at the site that were
similar to those calculated from light transmission data. The uncertainty of
chemical tracer data, both in the plume (because of uncertainty in sample
collection) and in the sludge (because historical data were used instead of
determining true values) results in uncertainty in the dilution calculations
from these data. Turbidity measurements inherently have lower uncertainty
associated with the data than chemical measurements because of the high
frequency of sampling and the relative simplicity of the measurement.
However, because of uncertainties in the physical behavior of sludge
particles in the marine environment (flocculation, dissolution), there is
4-43
-------
TABLE 4-8. ESTIMATES OF DILUTION AFTER T*0 h FOR SEWAGE SLUD5E PLUMES
STUDIED IN MARCH 1988.
Concentration (jig/L)
Plutte Metal T-Q h
T=x h
Tlae of
Sampling Additional
(T-x h) Dilution*
Overall
Rate of
Dilution**
(per hour)
DB1QC Cu
Pb
Zn
Fe
DBlld Cu
Pb
DB126
19.51
10,
17
191
0.40
0.40
1.57
1.04
1.41
14.0
NA
NA
4.3
4.3
4.3
4.3
12:1
10:1
12tl
14:1
DB13 Cu
Pb
Zn
Fe
DB14C Cu
Pb
Zn
Fe
DB15f Cu
Pb
Cu
Fe
7.5
34.5
35.7
117.1
12.4
9.7
19.5
154.2
4.9
2.4
6.35
50.6
2.9
13.5
12.5
39.4
0.43
0.27
1.44
3.21
1.33
0.15
2.82
1.36
1.3
1.3
1.3
1.3
1.0
1.0
1*0
1.0
0.5
0.5
0.5
0.5
3:1
3:1
3:1
3:1
29:1
36:1
13:1
48:1
4:1
16:1
2:1
37:1
14,400:1
11,000:1
5,500:1
--
— —
--
__
--
8,100:1
30,000:1
4,800:1
^Dilution after T-0 h; calculated as follows!
Concentration at T^G h divided by concentration at T=x h.
b (Concentration at T=0 h divided by concentration at T=x h)/Time of
sampling (x).
C0rigin of sludge unknown. Cannot calculate overall dilution,
tracer samples collected at T=0 h.
tracer samples from this plume.
fSamples were not collected for the particle maximum in the plume for last
samples collected. Therefore, the dilution estimates are overestimates.
4-44
-------
also a large uncertainty associated with calculation of sludge dilution from
turbidity. Therefore, both measurements complement each other and are
necessary for the determination of sludge dilution.
For reasons discussed previously, chemical tracer data from the
survey could not be used satisfactorily to calculate sludge dilution. As a
result, the determination of sludge dilution under winter conditions
requires further study in future surveys.
4*4.2>3 Plume Transport
Knowledge of the time required for sludge plumes to leave the 106-
Mile Site is of critical concern because water quality criteria must not be
exceeded at any time outside the site. In addition to direct measurements
of currents (XCP and drifter data), continual contact with the sludge plumes
during the various sampling events (DB-10 through DB-15) of the March 1988
survey provides another estimate of the rates at which plumes are being
advected. .Table 4-9 summarizes the speed and direction of sludge plume
transport for five of the six plume events surveyed during March 1988. No
data are provided for event DB-12 because the dumping occurred outside of the
site.
Table 4-9 indicates that the surface plumes moved to the north-
northeast, with the exception of plume DB-11, which moved toward the
northwest. Average transport speeds varied from 2 to 31 cm/s over the 2 days
of the survey. Using the average speed and direction of plume transport, the
time that would be required for each plume to cross the site boundary was
calculated directly As indicated in Table 4-9, these times ranged from 5 to
57 h, assuming that the currents would remain constant over the individual
time periods for each plume event. These times were based upon the transport
of the specific portion of the plume surveyed, rather than the part of the
plume that lies closest to the downstream site boundary. Nevertheless, this
analysis suggests that the five plumes did not cross the boundaries of the
106-Mile Site within 4 h after dumping. The slow transport resulted from
near-surface current conditions that were much less intense than (1)
currents observed during the nearfield survey in September 1987, and (2)
currents during the passage of warm-core eddies of Gulf Stream origin, which
4-45
-------
TABLE 4-9. SUMMARY OF PLUME TRANSPORT INFORMATION FOR PLUMES MONITORED
DURING THE MARCH 1988 SURVEY AT THE 106-MILE SITE.
Start Transport Transport Time to Cross
Event Date Tine Direction Speed (cn/s) Boundary (h)
DB-10 3/2 1212 17° 7 14
DB-11 3/2 2011 339° 2 5
DB-13 3/3 2006 34° 31 5
DB-14 3/4 0719 38° 15 9
DB-15 3/4 1102 28° 6 57
4-46
-------
are not uncommon at the site. Under these two conditions, plumes may be
advected out of the site within a few hours after dumping. During weak flow
condition, which may occur 60 to 80 percent of the time, dumping on the
leeward side of the site would ensure that plumes do not cross the site
boundaries within 4 h of dumping.
4.S MATER QUALITY MEASUREMENTS
Two concerns of the 106-Mile Site monitoring program are to verify
(1) that the adverse impacts of sludge dumping on water quality at the site,
as measured by increased metal and organic contaminant concentrations, and
increased pathogen counts, are not in excess of those permitted by the ocean
dumping regulations and permit requirements,* and (2) that sludge dumping has
no significant effect on dissolved oxygen levels at the site. The survey
addressed water quality issues through the analysis of water samples
collected in sludge plumes for contaminants for which there are water quality
criteria. Samples for measurement of these contaminants were collected in
five plumes at T*0 h. However, only one plume was sampled for water quality
parameters 4 h after disposal. Samples at 4 h could not be collected for
other plumes because surveying operations were terminated earlier due to the
small plume size or equipment difficulties. Contaminant concentrations have
also been calculated from transmissometry data for one plume. Monitoring of
dissolved oxygen was conducted with the Seabird CTD. All water quality data
are presented in Appendix C.
4.5.1 Caparison to Hater Quality Criteria
Analysis of samples collected within the sludge plumes at T=0 h
indicated that copper, lead, and mercury exceeded water quality criteria
immediately after discharge from the barge (Table 4-10), Copper exceeded the
criterion at T=0 h in all plumes except one; the lead criterion was exceeded
in three of the five plumes; and the mercury criterion was exceeded in two of
the five plumes. Pesticide/PCB concentrations were below water quality
criteria in all samples monitored. Samples collected within the plumes at
least 1 h after disposal suggested that all metal contaminants were
4-47
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TABLE 4-10. COMPARISON OF METAL MEASUREMENTS IN SLUDGE PLUMES DB-2 AND DB-3
APPROXIKATELY 4 h AFTER DISPOSAL AT THE 106-MILE SITE TO EPA
MARINE HATER QUALITY CRITERIA.
Plire
DB10
DB10
DB11
*- D313
k **
D614
DB14
D315
D315
Water
Saiple
Depth
M
1
4.5
2.5
1
3
2
4
1
2.5
Rep
T
2
1
2
1
1
1
1
1
1
Time
After
3 (h)
0.1
4.3
0
OJ
1.6
0
1
0
0.5
Quality Criteria
* *
1.410 0.149
1.314 0.053b
0.824 0.008*
1.287 0.096
2.033 0.144
1.896 0.107
36 2.3
W
0.323
0.04lb
'0.034
0.502
0.133
0.056
9.3
Cu Or
1*
19.51 9.09
1.56b 0.63
0.40 0.29
7.48 11.14
2.90
12.43 2.48
0.43
4J6 0.47
0.296
2.9 50
K*
J/L
190 J6
13.95^
2.97
117.05
39.35
154.22
3.21
50.59
1.36
m
Nl
2.395
0.435b
0.336
1.677
1.137
0.834
8.3
Fb Se
14.09 <0.036
l,04b
-------
at or below water quality criteria, with the exception of lead in DB-13,
which exceeded the water quality criteria 1.6 h following disposal.
However, for at least one plume (DB-13), it can be verified that
sampling for water quality measurements did not occur in the plume core.
Based on transmissometry observations, the core of plume DB-13 was
dispersing at a rate of 2,850/h (Table 4-6). Given this dispersion rate, the
plume would have been diluted 11,400-fold after 4 h. At this dilution,
copper and lead would be present at 10 /»g/L and 28 j»9/L» respectively; both
above water quality criteria.
This analysis of water quality parameters from turbidity measurements
provides an independent check on the chemical measurements^ made on actual
samples. Comparison of analytical results to water quality criteria are
predicated on the assumption that the volume of maximum contaminant
concentrations within the plume was always sampled. As with plume DB-13,
this did not always occur. Sampling in the sludge core might have revealed
higher concentrations of contaminants that may have exceeded water quality
criteria.
4.5.2 Clostrldlum perfrlngens
A microbiological tracer of sewage sludge, C^ perfrinqens. was found
at elevated levels in all sludge plumes sampled except DB-13 (Table 4-11).
Compared to the September 1987 survey, fewer samples had C^ perfringens
levels that were too numerous to count, indicating that shipboard processing
modifications provided more reliable data than obtained in the summer 1987
survey* As found during the summer 1987 survey, C^ perfringens
concentrations in sludge varied substantially among the various authorities
disposing sludge at the 106-Mile Site. No measurable C^ perfringens spores
were found in sludge plume DB-13; sludge originating from Passaic Valley.
Passaic Valley uses the Zimpro method of employing high temperature and
pressure for sludge dewatering. This treatment presumably was effective in
killing all C.. perfringens spores in the Passaic Valley sludge. Complete C^
perfringens data are presented in Tables C-2 in Appendix C.
4-49
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TABLE 4-11. CONCENTRATIONS OF C. perfrinqens IN THE
SLUDGE PLUMES AT T«0 h AND BETWEEN 0.5 AND 4
h AFTER DISPOSAL. (RESULTS ARE BASED ON THE
MAXIMUM OBSERVED IN THE SET OF REPLICATE
SAMPLES FOR THE SAMPLE PERIOD.)
Plune
DB-10
DB-11
OB- 13
OB-14
DB-15
T*0 h
420
3.5
0
TNTC
964
T-x h
34
NA
0
62
52
x (h)
4.3
-
1.6
1.0
0.5
TNTC - Colonies too numerous to count.
NA - Not available.
4-50
-------
4.5.3 Dissolved Oxygen
Using the same methods employed during the previous survey, dissolved
oxygen concentrations were monitored continuously during vertical and
horizontal profiling operations using an in situ oxygen probe interfaced to
the CTD/transmissometer profiling system. Results of these analyses agreed
with those of the September 1987 survey revealing that perturbations in
dissolved oxygen levels were at or below the resolution of the oxygen probe
(ca 0.1 ml/L) and that levels of dissolved oxygen in site waters were
essentially unaffected by sludge dumping. Because the effect of sludge
dumping on dissolved oxygen levels was so small, further analyses of oxygen
data were not made. Further characterization of dissolved oxygen at the site
would require that in situ profiling be supported with multiple oxygen
titration analyses, an effort that does not appear warranted based on data
from this survey and the previous survey.
4.6 DISSOLVED AND PARTICULATE CONTAMINANT DISTRIBUTION
Prediction of the long-term fate of sludge contaminants at the 106-
Mile Site requires an understanding of how the sludge contaminants partition
between dissolved and particulate phases after disposal. Nearfield
monitoring strategies are based on the assumption that sludge contamination
follows the particulate phase. However, sludge components found primarily
in the dissolved phase at the time of disposal or redistributing from the
particulate phase to the dissolved phase after disposal will not settle with
the particulate matter and thus may be transported from the disposal site by
different routes and at different rates than those components remaining in
the particulate phase. Therefore, depending on the rate of contaminant
redistribution, the current strategy of fate monitoring based on
transmissometry may not give a true account in the nearfield and may not be
completely effective in the farfield.
To examine the question of sludge partitioning after disposal,
samples for analysis of total and particulate metals were collected from the
sludge plumes as a function of time. The comparison of concentrations of
metals in both phases allows an assessment of sludge contaminant
4-51
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redistribution after disposal, information that is needed for resolving the
issue of contaminant redistribution. Only a limited number of samples and a
limited number of elements were analyzed for this preliminary study to
determine if redistribution occurred at the site. Cadmium, copper, iron,
lead, nickel, and zinc were analyzed in dissolved and particulate samples at
T=0 h, whereas only copper, iron, lead, and zinc were analyzed in samples
collected later during each event.
Because of the high particulate concentrations, most of the toxic
compounds and metals in the sewage sludge dumped at the 106-Mile Site were
initially associated with the solid (particulate) phase (Table 4-12).
Analysis of metal contaminants in the dissolved and particulate phases of
sludge plumes at the 106-Mile Site revealed the following regarding the
behavior of this metal contaminations
* At T=0 h, the relative amount of particulate to dissolved
metal was similar to, but somewhat lower than, that of the
original sludge values. The exceptions were nickel and
copper, which appeared to partition from the particulates
immediately upon disposal (Table 4-12).
* For all but one dumping event (DB-13), data for metals
indicated a selective partitioning of metal contaminants
from the particulate to the dissolved phase in the short term
(Table 4-13). Partitioning was element-specific, with iron
showing the least partitioning of the elements analyzed.
* Anomalous behavior of sludge from Passaic Valley (dumping event
DB-13) may be related to post-digestion high temperature and
pressure dewatering treatment (Zimpro process).
The apparent decrease in the fraction of the total metal associated
with the sludge particles after disposal implied that at least some metal
contamination moves from the particulate phase to the dissolved phase when
sludge is disposed in the ocean, most likely as a result of desorption of
metals from sludge particles. However, the percentage of the metal
originally associated with the sludge particles that is transferred to the
dissolved phase after disposal could not be determined because undiluted
sludge was not characterized in this study. The time scale of this
repartitioning appeared to be rapid, on the order of minutes to hours.
4-52
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TABLE 4-12. COMPARISON OF PARTITIONING OF METALS BETWEEN DISSOLVED AND
PARTICULATE PHASES IN SLUDGE DUMPED AT THE 106-MILE SITE.
UNITS ARE IN PERCENT OF THE ELEMENT IN THE PARTICULATE PHASE.
Pluae at T=0 h
Metal
Cd
Cu
Fe
Pb
N1
Zn
Sludge3
97-99.5
90-99
NA
95-99.8
80-95
92-98
DB-10
85
83
65-77
73-90
43-70
96
DB-11
NA
43
100
64-74
NA
100
DB-13
100
100
100
100
70
100
DB-14
57
52-81
54-74
55-75
21-28
64-113
DB-15
86
42-91
49-87
>80
14-23
79-100
Background
«25
6-10
44-100
2-60
0-13
NA
*Based on results included in the permit applications from the 9 sewerage
authorities applying for permits to dispose sludge at the 106-Mile Site.
4-53
-------
TABLE 4-13.
PARTITIONING OF METALS BETWEEN DISSOLVED AND PARTICULATE
PHASES IN SLUDGE DUMPED AT THE 106-MILE SITE AT TO AND AT
LEAST 1 h AFTER DISPOSAL. UNITS ARE IN PERCENT OF THE ELEMENT
IN THE PARTICULATE PHASE.
Metal
DB-10
DB-13
DB-14
h T*0 h T=1.6 N T*0 h T=l h
DB-15
T=0 h T=0.5 h
Cu
Fe
Pb
Zn
83
65-77
73-90
96
66
55
66
100
100
100
100
100
100
100
97
100
52-81
54-74
55-75
64-100
29
73-93
27-44
29-67
42-91
49-87
>80
79-100
33
89-100
33-56
18-32
4-54
-------
The dissolution of particulate metals (and presumably other
participate contamination) has several implications on the short- and long-
term fate of sludge dumped at the sites
* Short-term (0 to 24 h) settling of sludge may remove only a
portion of the contaminants from the ocean surface to the
region of the pycnocline. Other contamination may remain
dissolved in surface water,
* Transport vectors of contaminants on sludge particles may be
different than that of contaminants in the dissolved phase
because the particulate phases may settle into ocean regions
being transported in directions different than the surface
waters. This may be particularly important if ocean currents
at depth, where the particles will eventually reside, are
different from those at the ocean surface. Thus, long-term,
farfield fate monitoring programs (e.g., sediment
collections) must consider the diverse nature of the
transport pathways if detection of sludge components is to
be successful.
* Under certain oceanographic conditions of slow current
movement and limited turbulence, the nearly continuous sludge
disposal at the site (1 to 4 barges per day) may cause a
detectable increase in surface water contamination in and
adjacent to the site. The residual dissolved signal from the
sludge may be decreased only through mixing or relatively
slow natural depositional processes. If mixing is
relatively slow, dilution will not occur, increasing the
likelihood of elevated contaminant concentrations in the
site.
The partitioning of contaminants from particulate phase to dissolved
phase complicates farfield monitoring at the site. Because many
contaminants in a residual sludge plume are likely to be in the dissolved
phase, oceanic mixing will be the primary mechanism for decreasing the
contaminant concentrations in the surrounding seawater. Removal from the
ocean will be slow and by natural biogeochemical processes. Because the
natural removal processes are slow relative to the sludge settling, the
sludge contaminants in the residual plume may be transported far from the
disposal site before they are mineralized and deposited in the ocean
sediments. Thus, a farfield fate monitoring program to detect such
deposition would be difficult to design. Additionally, a residual plume of
4-55
-------
dissolved contaminants in the surface ocean would not be detected or measured
using transmissomery-based methods of plume tracking. Thus, the transport of
dissolved contaminants will be difficult to monitor with current tracking
methods. The transmissometer used to detect the particulate phases of the
sludge in the nearfield will certainly not detect the dissolved residual
phase of the sludge plume in the farfield. Only sophisticated sampling
techniques or widespread collection of seawater from numerous and widely
dispersed stations could detect the presence of dissolved contamination in
the farfield.
4.7 OBSERVATIONS OF CETACEANS *ND MARINE TURTLES
A total of 17 cetaceans (5 sightings) representing 3 species were
observed between March 1 and 5, 1988. Three sightings of fin whales
(Baleanoptera physalus) were made north of the site, and an additional
sighting was made within the boundaries of the site. Two non-endangered
species (pilot whales, Globicephala melaena, and bottlenosed dolphins,
Tursiops truncatus) were also observed throughout the study area. Cetacean
densities are presented in the site condition report ( EPA , 1988c).
There were no sightings of marine turtles during this survey.
4-56
-------
5.0 CONCLUSIONS
5.1 DISCUSSION OF NULL HYPOTHESES
Monitoring the nearfield fate of sludge plumes is one component of
Tier 2 monitoring activities presented in the 106-Mile Site monitoring plan
( EPA , 1992a). Nearfield fate monitoring addresses both permit
compliance and impact assessment. It addresses permit compliance because the
permits for disposal of sludges at the 106-Mile Site will stipulate that
water quality criteria (WQC), where they exist, may not be exceeded within
the site 4 h after dumping and outside the site at any time. When WQC do not
exist, the permits will require that the waste concentration not exceed a
factor of 0.01 of a concentration known to be acutely toxic after initial
mixing, i.e., the limiting permissible concentration (LPC). The combined
conformance to LPCs and WQC is thought to be protective of the marine
environment.
Nearfield fate (and short-term effects) monitoring also addresses
the potential for impacts within the immediate vicinity of the site and in
the short term, defined for convenience as 24 h. Nearfield fate
determinations address the horizontal and vertical behavior and movement of
sludge within and immediately adjacent to the site. Monitoring the behavior
and movement of sludge immediately after disposal is necessary to confirm
assumptions made about dispersion and dilution when issuing permits.
The 106-Mile Site monitoring plan ( EPA , 1992a) uses site and
waste characteristics to predict possible impacts of sludge disposal and
formulate testable null hypotheses that these predictions suggest. Results
of the survey are discussed in terms of hypotheses addressing issues
associated with Tier 2 of the monitoring plan. Where applicable, results of
this survey are compared to those of the previous survey to the 106-Mile
Site. The hypotheses Ho3 through H(j9 are divided into two categories;
permit compliance and impact assessment.
5-1
-------
Permit Compliance; Nearfleld Fate
Concentrations of sludge and sludge constituents outside
the site are below the permitted LPC and WQC at all
times. '
Because of low surface current drift at the
site during the time of the survey, sludge
plumes monitored at the site were not observed
to cross site boundaries during the March 1988
survey. Analysis of transport suggests that
water quality criteria would not be exceeded
outside the site for these plumes.
One barge was found dumping outside of site
boundaries. Concentrations of sludge and
sludge constituents probably exceeded permitted
levels for this plume.
H04i Concentrations of sludge and sludge constituents within
the site are below the permitted LPC and WQC 4 h after
disposal.
Concentrations of all sludge contaminants for
which there are warine WQC were below or
calculated to be below WQC 4 h after disposal,
as'determined by analysis of water samples in
sludge plumes. Dilution rates of plume cores
(most concentrated parcels) calculated from
transmissometry suggest that had samples been
collected in the plume core of DB-13, WQC would
have been exceeded for at least copper and
lead. Therefore, at least for this plume,
samples collected for water quality analyses
probably were not representative of the most
concentrated volume in the plume and therefore
WQC data for this survey may have
underestimated contaminant levels at the site.
H05: Pathogen levels do not exceed ambient levels 4 h after
disposal.
The microbial tracer, C. perfHnqens, exceeded
ambient levels in the only sludge plume sampled
at T=4 h. C. perfrinqens is not a pathogen,
but a conservative microbial tracer of sewage;
therefore, C, perfrinqens data are not
conclusive proof that pathogen levels are being
exceeded 4 h after disposal. Measurements of
£. perfringens suggested that this hypothesis
was false^direct measurements of pathogens
will be requried to prove it false.
5-2
-------
Impact Assessment: Nearfleld Fate
Ho6: Sludge particles do not settle in significant quantities
beneath the seasonal pycnocline (50 ra) or to the 50-ra
depth at any time, within the site boundaries or in an
area adjacent to the site.
Sludge was observed to penetrate the surface
pycnocline (between shelf and slope waters) and
descend to 80 m within 3 h after dumping during
one dumping event. The deep penetration may
have been related to a dumping rate in excess
of the court-ordered 15,500 gal/min. Sludge
dumped at the court-ordered rate of 15,500
gal/min or less was observed to remain within
the upper 25 m during winter oceanographic
conditions* This hypothesis was therefore
demonstrated to be false under the observed
conditions.
HO?; The concentration of sludge constituents within the site
does not exceed the LPC or WQC 4 h after disposal and is
not detectable in the site 1 day after disposal.
As stated in Ho4, sampling and analysis of
water samples for sludge constituents was
insufficient to determine if WQC were exceeded
4 h after disposal.
Some surface water collected for background
contaminant analysis contained metal
contaminant levels approaching or exceeding
WQC. The high levels probably resulted from
previous dumping activity at the site, although
this cannot be verified from the data. In the
absence of surface currents that would remove
surface contamination, the frequency of dumping
at the site creates the potential for
contaminants to accumulate in surface waters.
Although not observed, the rapid formation of
two fractions of sludge plumes (one containing
dissolved contaminants, the other containing
particulate matter) can be predicted from the
limited data set on dissolved and particulate
contaminants in sludge plumes. A plume of
dissolved contaminants would not disperse
rapidly under conditions observed at the site,
and the predicted presence of such a plume
5-3
-------
tntght be the cause of the elevated contaminant
levels observed in background samples.
Ho8: The concentration of sludge constituents at the site
boundary or in the area aijacent to the site does not
exceed the LPC or WQC at any time and is not detectable 1
day after disposal.
No plumes dumped in the site were observed to
cross site boundaries within 4 h during the
March 1988 survey.
It was estimated that one sludge plume
monitored outside the site could have easily
been monitored for over 24 h given the high TSS
levels and rate of dilution. The high TSS
levels were believed due to a dumping rate in
excess of the court-ordered maximum. This
hypothesis was probably false under the
conditions observed during the survey.
H09: The disposal of sludge does not cause a significant
depletion in the dissolved oxygen content of the water
nor t significant change in the pH of the seawater in the
area.
The observed depression in dissolved oxygen
levels in sludge plumes is minor and at the
limit of instrument resolution. During the
winter survey, pH was not monitored in sludge
plumes.
5.2 EVALUATION OF MEASUREMENT TECHNIQUES
The March 1988 survey was the second field application of proposed
technical guidance for plume-tracking activities to be conducted as part of the
106-Mile Site monitoring program, and the first to be conducted under winter
conditions. A secondary objective of the survey was to evaluate methods that
may be used in the future by EPA or by permittees. The following methods
(originally presented in Sections 2.0 and 4.0) are evaluated in terms of the
success of the March 1988 survey:
5-4
-------
Identification and tracking of a sludge plume with dye and
surface and subsurface drogues.
Both dye and drogues worked well for identifying a portion of
a sludge plume for surveying. Dye mixed in from the R/V
Endeavor resulted in only a surface expression, and thus
could not be used to monitor dispersion. Dye introduced from
the barge would be more useful as a sludge tracer.
Monitoring the movement and dispersion of the narked sludge
plume with visual observations from a survey vessel and a
aircraft.
All visual observations were successful in monitoring the
movement and dispersion of the plume. Aerial photo-
reconnaissance proved to be a useful tool for determining
the orientation and width of the plume during the first half
hour after dumping. However, difficulties in scheduling
dumping operations during daylight hours often precluded
aerial reconnaissance.
Acquisition of in situ transnrissotnetry data to monitor the
movement and dispersion of the plume.
As with the previous survey, transmissometry was the most
sensitive,and reliable real-time tracking method and provided
the most data for near-field fate analyses. Horizontal
transmissometry profiling (transmissometer on a V-fin
depressor) allowed continuous profiling while the ship was
underway and making reciprocal passes through the sludge
plume.
Development of data reduction algorithms to isolate and
manipulate transmissometry data from the plume (highest 10
percent transmissometry readings) was directed by the
requirement of the ocean dumping regulations to observe
concentrated parcels of plume water. This data reduction
capability has enhanced the value of transmissometry data and
was a significant addition to the analyses of the previous
survey.
Collection of samples for chemical and biological tracers
and total suspended solids to determine actual
concentrations of sludge components and dilution of these
components.
Sample collection was limited on the March 1988 survey
because (1) sample collection was isolated from profiling
activities (discrete sampling vs pumping), and (2) there were
technical difficulties with discrete sampling equipment.
Because of the limited number of samples and because the
sample collection was not mated to turbidity profiling,
5-5
-------
transmissometry data could not be related to sludge
constituents at the site. Therefore, chemical and biological
tracer and TSS data were not as valuable as those same data
collected on the previous survey*
Future nearfield fate surveys at the site should return to a
directed (by transmissometry) pumping system so that chemical
and biological tracer data and TSS can be used to calibrate
shipboard measurements. Such a directed pumping system would
enhance the defensibility of all of the data resulting from
the survey.
• Acquistion of satellite-derived ocean frontal analyses, CTD
profiles, and neasurements of current shear to determine the
oceanographic conditions that nay have impacted the data
generated during the survey*
In addition to providing critical information for post-
survey data analysis, the above oceanographic measurements
also provided data that were extremely useful at sea for
predicting sludge plume behavior. CTD profiles and current
shear measurements proved necessary for interpretation of
nearfield fate data.
• Acquisition of real-time navigation data to support plume-
tracking activities.
Real-time navigation provided critical information necessary
for positioning the ship during plume tracking. By showing
the position of the ship in relation to the plume, real-time
navigation was an indispensible aid to the plume-tracking
survey.
5-6
-------
6.0 REFERENCES
Bisson, J.W. and V.J. Cabelli. 1979, Membrane Filter Enumeration
Method of Clostridium perfrlnqens. Applied Environmental
Microbiology. 37:55-66.
Cabelli, V.J. and D. Pedersen. 1982. The movement of sewage sludge
from the New York Bight dumpsite as seen from Clostridium
perfrinaens spore densities. In: Conference Proceedings of the
Marine Pollution Sessions of Oceans *82. Pp. 99S-999. Marine
Technology Society and the Institute of Electrical and Electronic
Engineers Council on Ocean Engineering, Washington, DC.
Csanady, 6.T. 1981. An analysis of dumpsite diffusion experiments.
In: Ocean Dumping of Industrial Wastes. Ketchum, Kester, and Dark
(eds.), Plenum Press, NY. 12:109-129.
Cranston, R.E. and J.W. Murray. 1977. The determination of chromium
species in natural waters. Anal. Chem. 99:275-282.
Danielsson, L., 8. Hagnusson, S. Westerlund, and K. Zhang. 1982. Trace
metal determinations in estuarine waters by electrothermal atomic
absorption spectrometry after extraction of dithiocarbamate
complexes into freon. Anal. Chim. Acta 144:183-188.
EPA. 1987a. Strategy for Plume Tracking Methods at the 106-Mile Site.
Environmental Protection Agency Oceans and Coastal Protection
Division (formerly OMEP), Washington, DC.
EPA. 1987b. Analytical Procedures In Support of the lOi-Mils Deepwater
Municipal Sludge Site Monitoring Program. Environmental
Protection Agency Oceans and Coastal Protection Division (formerly
OMEP), Washington, DC.
EPA. 1987c. Final Report on Analysis of Baseline Seawater and Sediment
Samples from the 106-Mile Oeepwater Municipal Sludge Site.
Environmenta1 Protection Agency Oceans and Coastal Protection
Division (formerly OMEP), Washington, DC,
EPA, 1987d. Draft Initial Survey Report for Plume Tracking Survey for
the 106-Mile Deepwater Municipal Sludge Site in Support of the EPA
106-Mile Site Monitoring Program. August 29 - September 5, 1987.
Environmental Protection Agency Oceans and Coastal Protection
Division (formerly OMEP), Washington, DC.
EPA. 1987e. Site Condition Report for Plume Tracking Survey for the
106-Mile Deepwater Municipal Sludge Site in Support of the EPA
106-Mile Sit^ Monitoring Program. August 29 - September 5, 1987.
Environmental Protection Agency Oceans and Coastal Protection
Division (formerly OMEP), Washington, DC.
6-1
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EPA. 1987f. Final Report on Analytical Results of Samples Collected
During the 1985 North Atlantic Incineration Site (NAIS) Survey.
Environmental Protection Agency Oceans and Coastal Protection
Division (formerly OMEP), Washington, DC.
EPA. 1988. Final Report of Analytical Results of the 106-Mile
Deepwater Sludge Dumpsite Survey-Summer 1986. Environmental
Protection Agency Oceans and Coastal Protection Division (formerly
OMEP), Washington, DC.
EPA, 1992a. Final Draft Monitoring Plan for the 106-Mile Deepwater
Municipal Sludge Site. Environmental Protection Agency. EPA 842-
S-92-009.
EPA. 1992b. Final Draft Implementation Plan for the 106-Mile Deepwater
Municipal Sludge Site Monitoring Program. Environmental
Protection Agency. EPA 842-S-92-01Q
6111, S.A. and W.F. Fitzgerald. 1987. Picomolar mercury measurements
in seawater and other materials using stannous chloride reduction
and two-stage gold amalgamation with gas phase detection. Mar.
Chem. 20:227-243.
Higgins, I.J. and R.Q Burns. 1975. The Chemistry and Microbiology of
Pollution, Academic Press, New York, NY. 148 pp.
O'Connor, T.P., H.A. Walker, J.F. Paul, and V.J. Bierman. 1985. A
Strategy for Monitoring of Contaminant Distributions Resulting
From Proposed Sewage Sludge Disposal at the 106-Hlle Ocean
Disposal Site. Mar. Env. Res. 16:127-150.
Santoro, E.D. and J.J. Fikslin. 1987. Chemical and Toxicological
Characteristics of Sewage Sludge Ocean Dumped in Mew York Bight.
Marine Pollution Bulletin. 18(7):394-399.
Stumm, M., and J.J. Morgan. 1981. Aquatic Chemistry, 2nd edition, John
Wiley, New York, NY. 780 pp.
6-2
-------
APPENDIX A
DATA QUALITY REQUIREMENTS AND OBJECTIVES
-------
A.I DATA QUALITY REQUIREMENTS AND OBJECTIVES
The data requirements for chemical analysis are summarized in Table 3-2.
Accuracy of the chemical results was determined by analysis of procedural
blanks, matrix spikes, and certified reference materials, when reference
materials were available. Selected samples were also spiked with known amounts
of the analyte of interest and the recovery of the spike monitored to determine
extraction efficiencies. For organic compounds, both field and laboratory
extraction efficiencies were monitored through addition of surrogate compounds.
Precision of analysis was determined by analysis of duplicate samples.
The accuracy of Clostridium perfringens, particulate trace metal, and
total suspended solids (TSS) results could not be evaluated because certified
/
reference standards are not available and spiking samples for these parameters
was not feasible.
».2 QUALITY COHTROl RESULTS
A.2.1 Total Suspended Solids
Analysis of duplicate TSS samples showed high relative percent difference
(RPD) that exceeded the quality control objectives for this analysis. The high
RPD was probably due to the settling of particles in the Go-Flow bottles prior
to removal of the samples. Two field procedural blanks indicated field
conditions may have contributed between 0.03 and 16 mg to each TSS
determination. Because the field blank was variable, TSS results were not
corrected for the blank contribution.
A.2.2 Hetals
The method detection limits determined during the analysis of the samples
for trace metal concentrations are listed in Table A-l. Except for selenium,
the method detection limits were sufficient to quantify the concentration of
the metals at background oceanic levels. With one exception, detection limits
achieved were within the objectives for this project. Arsenic concentrations
at the site were well above the detection limit achieved, allowing this element
A-l
-------
to be quantified in all samples. Results of procedural blanks (Table A-2)
indicate metals were processed and analyzed without significant contribution of
contaminants to the sample. A consistent contribution froi the analytical
procedures was found for cadmium, iron, mercury, and zinc. Sample results were
corrected for these blanks. Analysis of sample duplicates indicated excellent
precision (<15 percent as the RPD) was obtained in the laboratory (Table A-3).
The precision of the chromium (31% as the RPD) analysis was approximately twice
that listed in the data requirements objective. Precision estimates for zinc
were not obtained due to an anomalous zinc concentration in one of the sample
replicates.
Recoveries of matrix spikes (Table A-4) were excellent. The recoveries
ranged between 75"and 121 percent of the known addition for most metals. Low
recoveries of silver («54%) were observed. Iron recoveries were variable.
Significant overrecovery was not observed for any metal, indicating
contamination-free processing of the samples. Metal recoveries from certified
seawater samples (Table A-5) were in the same range observed for the matrix
spikes (77 to 131%). Silver, mercury, and selenium were not certified in
standard seawater, therefore no estimate of accuracy was available from this
quality control check.
Certified reference material is not available for marine particulate
matter. Also, collection of a sufficient mass of particulate matter to enable
spiking of the particulate samples was not practical. Therefore, accuracy
checks on the recovery efficiency of the particulate method are not available.
Estimates of precision for duplicate particulate metal samples (Table A-6)
ranged between 24 to 166 percent as the RPD (Table A-7). Iron had a higher RPD
than any of the other metals. A small and variable amount of contamination
from the analytical procedures was observed in procedural blanks for most of
the metals. This variability may have caused some of the observed variability
in the particulate metal results. However, variability observed in the
particulate metal results was more likely due to heterogeneity of the water
within the Go-Flow sampling bottle.
A-2
-------
A.2 ORGANIC COMPOUNDS
Hethod detection limits for the pesticide
(PCB) analysis are shown in Table A-8. Detect
generally 10 times lower than listed in the an
survey. Recoveries of organic compounds were
extraction procedure, during field extractions
Field recoveries were determined by the addition of a known amount of
deeachlorobiphenyl to each sample during sampl
vessel. The recoveries determined for this conpound were low and variable
(Table A-9), ranging between 12 and 53 percent
and polychlorinated biphenyl
on limits achieved were
alytical objectives for this
determined at two steps of the
and within the laboratory.
s extraction on the survey
Sample results were not
corrected for this extraction efficiency. In the laboratory, analysis of a
blank spike containing a suite of compounds wa
Recovery of compounds from the two spiked samp
exception of Cl2(8). The results indicate tha; the cleanup step (silica-
alumina column chromatography) used to remove
successful. Replicate analysis of one extract
those compounds detected in each sample split
conducted (Table A-10).
es was excellent with the
nterfering organic compounds was
gave excellent precision for
[Table A-ll).
A-3
-------
TABLE A-l. METHOD DETECTION LIMITS FOR AHALYSIS OF SAMPLES
FOR TRACE METAL CONCENTRATIONS DURING NEARFIELD
MONITORING SURVEY MARCH 1988.
Detection Liait 0»g/L)
Analyte Whole Hater Particulatesa
Arsenic
Cadmi urn
Chromium
Copper
Iron
Lead
Mercury
Nickel
Selenium
Silver
Zinc
0.062
0.001
0.006
0.009
0.03
0.004
0.00003
0.05
0.04
0.002
0,004
NA
0.003
NA
0.010
0.06
0.005
NA
0.007
NA
NA
0.03
NA - Samples not analy2ed for these metals.
afiased on 500 nsL sample volume.
A-4
-------
TABLE A-2. RESULTS OF PROCEDURAL BLANKS ANALYZED WITH TRACE METAL SAMPLES,
NANOGRAMS OF METAL CONTRIBUTED TO EACH SAMPLE.
Sample
Type
Ag
As
Cd
Cr
Metal
Cu Fe jig
Whole water samples
Water
Quality
Tracer
0.35
0.34
0.34
NA
NA
NA
<.31
NA
NA
NA
NA
NA
<.78
<.68
NA
NA
NA
NA
1.05
<.90
<.90
NA
NA
NA
<1,7 14.4 0
<1.7 11.0 0
NA NA 1
<1.6 26.6 1
<1.6 23.0 1
2.2 38.2 1
Participate Field Blanks
NA
NA
NA
NA
<1.1
2.8
NA
NA
<4.7 240
<4.7 120
42
26
A
A
A
A
NA
NA
Ni
<9.4
<9.4
NA
NA
NA
NA
<3.3
6.3
Pb
<.70
<.70
NA
<1.2
1.5
2.4
12.2
7.7
Se
<1.6
NA
NA
NA
NA
NA
NA
NA
Zn
NA
3.78
NA
8.8
11.0
12.9
524
768
NA = Not available for this sample.
A-5
-------
TABLE A-3. PRECISION OF DUPLICATE SAMPLE ANALYSIS PRECISION REPORTED AS THE RELATIVE PERCENT DIFFERENCE (RPD).
Source Time
Plume (h)
(Depth)
Aga Asa Cd Cr*
Cu
Metal
Fe Hg
Ni
Pb
Se Zn
Whole Water, pg/L
DB10 4.3
DB10 4.3
MEAN
%RPD
DB13 1
DB13 1
mean
%RPD
Particulatesc
DB10 4.3
DB10 4.3
Mean
%RPD
(4.5)
(4.5)
(5)
(5)
. A9/L
(4.5)
(4.5)
0.0077 0.809 0.044 0.44
0.0090 0.839 0.038 0.32
0.0083 0.824 0.041 0.38
16 4 15 31
_ _ _ _
_
_
-
0.021
0.028
0.025
28
1.54
1.57
1.56
2
3.23
3.45
3.34
6
0.88
1.17
1.03
28
13.87 NA
14.03 NA
13.95
1
43.98
39.89
41.94
10
1.30
14.1
7.69
17
0.417
0.453
0.435
8
_
-
-
-
0.183
0.121
0.152
39
1.037
1.036
1.036
0
15.34
16.83
16.08
9
0.493
0.879
0.690
56
<0.066 17.99
<0.069 1.41
-
NA NA
15.08
15.50
15.29
3
1.34
1.71
1.53
24
aplume DB-11, Replicate 1, 2.5 m, 0 h after disposal.
bPlume DB-11, Replicate 2, 2.5 m, 0 h after disposal.
CField duplicate from one sample bottle.
-------
TABLE A-4. RECOVERY OF METALS FROM HATER SAMPLES SPIKED WITH KNOWN AMOUNTS
OF METAL. RECOVERIES MERE DETERMINED FOR A SAMPLE COLLECTED IN
PLUME DB-10 it T=4.3 h AND 4,5 l DEPTH UNLESS OTHERWISE NOTED.
UNITS ARE IN PERCENT RECOVERED.
Metal
Sample
Type Ag As Cd
Cr Cu Fe Hg Ni Pb Se Zn
Water 59* 105* 106 77 121 100 84b 100 101 117 98
Quality 51* 7?b
54* 75b
Tracer
113C
HOC
117C
aSpike to sample from plume DB11; sample T*0 h, 2.5 in, replicate 2.
bfllank spike recoveries.
cspike to sample from DB13, T=1.2 h, 5 m, Replicate 1.
A-7
-------
TABLE A-5. RECOVERY OF METALS (PERCENT) FROM STANDARD REFERENCE SEAHATER
(CASS-1) ANALYZED WITH EACH BATCH OF EXTRACTED SAMPLES.
Metal
Sample
Type Ag As Cd
Water a - 77
Quality a 98 77
-
*» *|* HIM
Tracer -
Samples -
Cr
126
114
103
107
..
-
Cu
117
117
m
*k
121
115
Fe
91
86
-
-
131
109
Hg Ni
a 107
a 107
B MB
4H *»
•ft m
«
Pb
99
101
Ml
-
96
89
Se
a
a
-
-
M
-
Zrt
109
109
-
-
104
97
aCASS-l is not certified for these elements.
A-ft
-------
TABLE A-6. QUALITY CONTROL RESULTS FOR TOTAL SUSPENDED SOLIDS ANALYSIS.
Sample Quality Control Units Result
Type Parameter
TSS Blank, Field mg 0.03
Blank, Field ing 0.16
TSS Replicate %RPO 23 & 1.0 rag/L
Replicate %RPD 12 6 7.8 mg/L
Replicate %RPD 34 i 2.3 rag/L
A-9
-------
TABLE A-7. QUALITY CONTROL RESULTS FOR PARTICULATE METALS ANALYSIS.
Metal
Parameter Units Cd Cu Fe Ni Pb Zn
Field ng <1.1 <4.7 240 <3.3 12.2 524
Blank ng 2.8 <4.7 120 6.3 6.7 768
Replicate* %RPD 31 28 166 40 57 24
aplume DB-10, 4.5 h after disposal.
A-10
-------
TABLE A-8. METHOD DETECTION LIMITS OF ORGANIC COMPOUNDS FROM 100-L
SAMPLES DURING THE 106-MILE SITE SURVEY, MARCH 1987.
Analyte
Cl2(8)
C13(18)
Cl3(28)
Heptachlor
Cl4(52)
Aldrin
C14(44)
CU(66)
Endolsulfan I
Dieldrin
pfp' DDE
Endrin
Endolsulfan II
Cl5(101)
p,p' ODD
C16{153)
Cls(105)
p.p1 DDT
Cl6(138)
Cl7(187)
Cl6(128)
Cl7(180)
Cl7(170)
Cl8(195)
Clg(206)
Detection Limit (ng/L)
0.09
0.03
0,07
0.05
0.03
0.08
0.04
0.06
0.08
0.11
0.12
0.11
0.10
0.04
0.15
0,04
0.17
0.18
0.06
0.12
0.19
0.01
0.02
0.01
0.01
A-ll
-------
TABLE A-9. FIELD RECOVERIES OF DECACHLOROBIPHENYL.
Plume
or
Event
BG-1
BG-1
BG-2
BG-2
DB-13^
OB-13^
DB-14
DB-14
DB-15
DB-15
Depth
65
65
16
16
5
5
4
4
2
2
Rep.
No.
1
2
1
2
1
2
1
2
1
2
Time
After Percent
T=0 (h) Recovery
28.1
39.2a
31.5
32.7
12.3
27.5
53.0
36.3
36.8
14.1
aMean of two analytical replicates.
^Sample filtered prior to extraction,
A-12
-------
TABLE A-10. RESULTS OF BLANK SPIKE ANALYSIS, ORGANIC COMPOUNDS.
Percent
Analyte Rep. 1
Pesticides
Heptachlor 117
Aldrin 374
Endolsulfan I NA
Dieldrin 124
p.p1 DDE 140
Endrin 134
Endolsulfan II NA
p.p' DDD 126
p.p' DDT 136
PCBs
Cl2(8) 35
Cl3(18) 98
Cl3(28) 110
CU(52) 102
Cl4(44) 113
Cl4(66) 109
Cl5(101 91
C16(153 111
Cl5(105 125
Cle(138 113
Cl7(187 94
Cl6(128 118
Cl7(180 110
Cl? 170 140
Cla 195 119
Clg 206 91
Recovery
Rep. 2
115
118
NA
139
121
121
NA
158
149
22
102
113
97
100
104
84
103
104
109
92
101
109
122
111
113
A-13
-------
TABLE A-ll. RESULTS OF REPLICATE ANALYSIS OF EXTRACTED SAMPLES.
SAMPLE WAS COLLECTED AT STATION BG-1, 65 n.
Analyte
Analytical Result (ng/L)
Rep. 1 Rep. 2
Percent
Difference
Pesticides
PCBs
Heptachlor
Aldrin
Endolsulfan I
Dieldrin
p,p' DDE
Endrin
Endolsulfan II
P,p'
p,p'
DDT
C12
C13
Cl3
C14
C16
C17
C17
C17
CIS
C19
8)
18)
28)
52)
44)
66)
101
153
105
138)
187
128
180
170)
195)
206)
DBOFB
0.135
NA
0.215
NA
NA
AN
NA
NA
NA
0.297
0.291
NA
NA
NA
NA
NA
NA
NA
0.088
NA
NA
NA
NA
NA
NA
105
0.136
NA
0.219
NA
NA
NA
NA
NA
NA
0.301
0.317
NA
NA
NA
NA
NA
NA
NA
0.088
NA
NA
NA
NA
NA
NA
104
0.74
1.86
1.35
8.93
0.0
A-14
-------
APPENDIX B
SUWARY OF BACKGROUND STATIONS DATA AT THE 106-HILE SITE
MARCH 1988
-------
TABLE B-l. TOTAL SUSPENDED SOLIDS, TURBIDITY, AND BEAM ATTENUATION RESULTS
FOR DISCRETE SAMPLES COLLECTED IN BACKGROUND HATER DURING THE
HARCH 1988 106-HILE SITE SURVEY.
Event
BG1
BG2
Depth
(n)
5
5
60
60
98
6
5
48
47
Sample Time
Replicate
I 0857
2 0857
1 0822
2 0822
1 0844
1 1225
2 1245
1 1339
2 1350
Time After
Disposal (h)
NA
NA
NA
NA
NA
NA
NA
NA
NA
TSS
<*/U
0.66
0.70
0.49
9.32*
0.80
0.36
0.38
0.46
0.39
Light
Transmit
83.3
83.3
85.5
85.5
87.4
83.1
83.4
85.2
85.2
Beam
Attenuation
0.731
0.731
0.627
0.627
0.539
0.453
0.439
0.641
0.641
aResult is inconsistent with other samples and is Hkely due to sample
processing.
B-l
-------
TABLE i-2, C, perfringens EHUMERATION IK SAMPLES COLLECTED FROM BACKGROUND
WATERS DURING THE MARCH 1988 106-MILE SITE SURVEY.
Plume
Background
3-2-88
Background
3-3-88
Depth
5
60
98
5
48
Counts
Repl. 1
0
0
0
0
0
per 100
Repl. 2
0
0
0
0
0
B|_a
Meanb
0
0
0
0
0
aColonies were enumerated following APHA guidelines for "Microbial Analysis
of Seawater and Marine Organisms". TNTC indicates that the colonies were
too numerous to count.
derived from a single count.
B-2
-------
OO
I
U)
TABLE B-3. SUMMARY OF TRACE METAL CONCENTRATIONS FOR UNFILTEREO HATER BACKGROUND SAMPLES COLLECTED DURING
THE MARCH 1988 106-MILE SITE SURVEY*
Station
BG1
BG1
BG1
BG1
BG1
BG2
BG2
BG2
BG2
Depth
n
5
5
60
60
98
6
5
48
47
Rep
1
2
1
2
I
1
2
1
2
Time
NA
NA
NA
NA
NA
NA
NA
NA
NA
As
1.373
1.519
1.335
1.217
0.934
1.434
Ag
0.0022
0.0018
0.044
0.0026
0.0021
0.0028
Cda
0.023
0.022
0.023
0.024
0.021
0.018
Cu
1.68
1.09
0.25
0.35
6.41
0.21
0.24
0.19
0.22
Cr
0.13
0.15
0.15
0.14
0.14
0.13
FC*
*I/L
6.03
4.53
2.58
2.47
41.11
0.38
0.27
0.36
1.68
N1
0.273
0.257
0.288
0.279
0.297
0.256
Pb
0.643
3.851
0.109
0.137
3.604
0.092
O.Q56
0.345
0.134
Se
<0.036
<0.036
<0.037
<0.036
<0.038
O.037
Zna
3.80
1.30
1.22
1.37
16.06
0.42
0.43
0.22
0.25
Hg
ng/L
7.6
7.9
3.4
8.3
4.9
3.7
aBlank corrected.
-------
TABLE B-4. SUMMARY OF PARTICULATE HETAL RESULTS FROM SAMPLES COLLECTED FROM
THE BACKSROUND HATERS DURING THE MARCH 1988 106-MILE SITE SURVEY.
UNITS ARE IN jig/L.
Station
BG1
BG1
BG1
BG1
BG1
BG2
BG2
BG2
BG2
Depth
(»)
5
5
60
60
98
6
5
48
47
Rep
1
2
1
2
1
1
2
1
2
Time
(h)
NA
NA
NA
NA
NA
NA
NA
NA
NA
Cd
0.0046
0.0043
0.0054
0.0121
0.0058
0.0069
0.0050
0.0056
0,0046
Cu
0.137
0.065
0.028
0.111
0.38
0.015
0.014
0.015
0.023
Fe
2.66
1.99
1.915
8.53
21.08
0.8
0.45
0.72
1.42
Ni
0.021
0.028
0.007
0.034
0.017
0.017
0.005
<.0047
<.0044
Pb
0.059
0.066
0.042
0.081
0.826
0.040
0.048
0.034
0.04?
Zn
0.99
1.63
0.25
0.87
1.05
0.61
1.15
0.59
1.41
B-4
-------
TABLE B-5. BACKGROUND WATER QUALITY PESTICIDE ANALYSIS, 106-MILE SITE, MARCH
1988. (NO OTHER PESTICIDES WERE FOUND IN THE BACKGROUND
SAMPLES.)
Depth
Station (o) Rep
Pesticide
Concentration
(ng/L)
Bi-1
BG-2
65
16
1
12
Endosulfan I
Dieldrin
0.15
0.60
B-5
-------
TABLE B-6. BACKGROUND HATER QUALITY PCB ANALYSIS STATIONS FOR THE 106-MILE
SITE SURVEY. MARCH 1988. (NO OTHER PCBs MERE FOUND IN THE
BACKGROUND SAMPLES.)
Station
Bfi-1
BG-2
Depth
65
16
Rep
1
2
Concentration
PCB (ng/L)
Clfi(138) 0.254
Cl7(180) 0.406
B-6
-------
APPEHDIX C
SUWARY OF LABORATORY DATA FROM PLUMES DB10. DB11. DB13. DB14, AND
DB15 SURVEYED^AT THE 106-MILE SITE IN MARCH 1988
-------
TABLE C-l. TOTAL SUSPENDED SOLIDS, TURBIDITY, AND BEAM ATTENUATION RESULTS
FOR DISCRETE SAMPLES COLLECTED DUMPING EVENTS, MARCH 1988
106-MILE SITE SURVEY.
Event
OB10
DB11
DB13
DB14
DB15
Depth
(*)
1
1
4.5
4.5
2.5
2.5
5
1
5
5
3
0
0
0
0
0
0
0
0
2
2
1
2
3
4
1
2
0.5
1.5
1.5
2.5
Sample Tine After
Replicate Tine Disposal (h)
1
2
1
1
1
,2
1
1
1
1
1
1
2
1
2
1
2
1
2
1
2
1
1
1
1
'1
1
1
1
1
1
1217
1217
1635
1635
2012
2012
2007
2025
2115
2119
2141
2137
2137
2151
2151
2157
2157
2220
2220
0719
0721
0737
0737
0821
0821
1103
1103
1119
1119
1133
1133
0.1
0.1
4.3
4.3
0
0
0
0.3
1.2
1.2
1.6
1.5
1.5
1.8
1.8
1.9
1.9
2.3
2.3
0
0
0.3
0.3
1
1
0
0
0.3
0.3
0.5
0.5
Light
TSS Transnrit
(n»g/L) {%)
8.00
7.50
1.13
0,90
1.09
1.71
1.17
18.5
16.9
12.1
8.00
9.12
26.6
8.23
7.33
1.84
2.16
1.93
2,73
5,68
1.26
8.46
2,00
0.92
0.29
2.10
0.74
1.41
3.83
0.58
2.97
19.4
19.4
78.4
78.4
NA
NA
76,5
0.2
2.5
10.7
11
14
14
57.7
57,7
47.5
47.5
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
Beam
Attenuation
(«-l)
6,243
6.243
0.913
0.913
1.072
24,193
14.756
8.94
8.829
7.864
7,864
2.2
2.2
2.978
2.978
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
C-l
-------
TABLE C-2. C. perfringens ENUMERATION IN DISCRETE SAMPLES COLLECTED
DURING DUMPING EVENTS. MARCH 1988 106-MILE SITE SURVEY.
Plume
DB10
Time
(h)
0.08
4.3
Depth
1
5
Counts per 100 nL
Repl. 1 Repl. 2 Mean*
420 420 420
34 34
DB11 0.00 2.5 2 5 3.5
DB13 0.00 5 0-0
0.32 1 0-0
0.90 5 0-0
1.15 5 0-0
1.22 5 0 - 0
1.58 3.1 0-0
DB14 0 - 2 TNTC TNTC TNTC
0.30 1-2 67 55 61
1.00 3-4 40 83 62
DB15
0
0.27
0.50
1-2
0.5-1.5
1.5-2.5
1200
388
47
729
729
57
964
558
52
Colonies were enumerated following APHA guidelines for
"Microblal Analysis of Seawater and Marine Organisms."
TNTC indicates that the colonies were too numerous to
count.
aMean derived from a single count.
C-2
-------
TABLE C-3. SUMMARY OF TRACE METAL RESULTS FOR WHOLE HATER SAMPLES COLLECTED DURING DUMPING EVENTS, MARCH 1988
106-MILE SITE SURVEY.
o
Plume
DB10
DB10
DB10
DB11
DB11
DB13
DB13
DB13
DB13
DB13
DB14
DB14
DB14
DB14
DB14
DB14
DB15
DB15
DB15
DB15
OB15
DB15
Sample
Depth
(•0
1
1
4.5
2.5
2.5
5
1
5
5
3
2
2
1
2
3
4
1
2
0.5
1.5
1.5 *
2.5
Rep
1
2
1
1
2
1
1
1
1
1
1
2
1
1
1
1
1
1
1
1
1
1
Time
Aftei
T=0 h
0.1
0.1
4.3
0
0
0
0.3
1.2
1.2
1.6
0
0
0.3
0.3
1
1
0
0
0.3
0.3
0.5
0.5
As
1.44
1.41
1.31
1.23
0.82
1.37
1.29
2.03
1.72
1.90
1.48
A§
0.157
0.149
0.0069
0.0083b
0.010
0.096
0.144
0.041
0.107
0.096
Cda
0.251
0.323
0.04lb
0.033
0.034
0.036
0.502
0.133
0.040
0.056
0.048
Cu
15.11
19.51
1.56b
0.36
0.40
0.39
7.48
6.83
3.34b
2.90
12.43
1.73
0.60
0.39
0.36
0.43
4.86
1.86
1.34
0.946
0.340
0.296
Cr
7.30
9.09
0.63
0.38b
0.29
0.28
11.14
2.48
0.38
0.47
0.39
Fe«
*9/L
153.3
190.9
14. Ob
2.96
2.97
3.37
117.1
93.3
41. 9b
39.4
154.2
22.3
11.3
3.2
2.5
3.2
50.6
24.6
18.2
13.0
1.33
1.36
Ni
1.723
2.395
0.435b
0.322
0.336
0.323
1.677
1.137
0.343
0.884
0.378
Pb
10.602
14.091
1.036b
0.396
0.378
0.807
Se
<0.037
<0.036
<0.038b
<0.038
<0.038
0.112
34.462 <0.052
30.98
16.08b
13.53
9.660
1.455
0.386
0.353
0.354
0.270
2.132
0.435
0.386
0.286
0.150
0.089
<0.039
<0.038
<0.038
<0.040
Zna
14.76
17.23
1.41C
1.25
1.51
1.21
35.73
31.50
15.29&
12.46
19.48
2.95
28.81
2.51
1.09
1.44
6.35
3.63
2.88
1.87
2.82
1.38
Hg
ng/L
40.5
9.1
6.6
5.6
4.7
19.2
88.3
29.8
4.8
10.2
8.4
aB1ank corrected.
bMean of replicate analysis.
cpuplicate rejected due to suspect contamination.
-------
TABLE C-4. SUMMARY OF PARTICULATE METAL RESULTS FROM SAMPLES COLLECTED
DUR1RS DUMPIHS EVENTS, MARCH 1988 106-MILE SITE SURVEY.
Station
DB10
OB10
DB10
OB11
OB11
DB13
DB13
DB13
DB13
DB13
D814
DB14
DB14
DB14
DB14
DB14
DB15
DB15
DB15
DB15
DB15
DB15
Depth
1
1
4.5
2.5
2.5
5
1
5
5
3.1
2
2
1
2
3
4
1
2
0.5
1.5
1.5
2.5
Rep
1
2-
1
1
2
1
1
1
1
1
1
2
1
1 .
1
1
1
1
1
1,
1
1
Tine
(h)
0.1
0.1
4.3
0
0
0
0.3
1.2
1.2
1.6
0
0
0.3
0.3
1
1
0
0
0.3
0.3
0.5
0.5
Cd
0.2333
0.2575
0.0246
0.0124
0.0139
0.012
0.500
0.466
0.174
0.184
0.076
0.017
0.0081
0.051
0.0088
0.0075
0.050
0.041
0.025
0.0085
0.0073
0.0099
Cu
13.47
14.8
1.03
0.15
0.18
0.169
12.83
12.94
4.19
4.78
6.5
1.4
0.19
0.097
0.11
0.12
2.05
1.7
0.73
0.43
0.094
0.11
Fe
M
118.4
123.75
7.69
3.68
3.35
2.44
123.08
111.89
40.47
43.24
83.04
16.45
6.84
3.63
2.3
2.35
24.55
21.3
12,46
5.06
1.18
1.38
Ni
'I
1.182
1.025
0.152
0.055
0.11
0.02
1.177
1.109
0.364
0.361
0.318
0,071
0.031
0.044
0.014
0.023
0.122
0.087
0.048
0.027
0.017
0.025
Pb
9.600
10.350
0.690
0.290
0.240
0.354
37.51
36.97
12.43
13.17
5.30
1.09
0.18
0.18
0.10
0.12
0.38
0.38
0.24
0.11
0.050
0.051
Zn
13.83
16.50
1.53
5.06
1>53
1.28
44.61
38.17
14.08
14.16
12.48
3.34
1.41
8-95
0.73
0.42
5.00
4.43
3.37
1.08
0.50
0.44
C-4
-------
TABLE C-5. SUMMARY OF PESTICIDE RESULTS FOR WHOLE HATER SAMPLES
COLLECTED DURING DUMPING EVENTS, MARCH 1988 106-MILE SITE
SURVEY.
Tine
Sample After
Plume Depth Rep Disposal Dieldrin p.p'DDE
(«) (h) (ng/L) (ng/L)
DB13 5 1 0 ND NO
DB13 520 0.31 ND
DB14 4 1 0 0.124 0.267
DB14 4 1 0 0.125 0.223
DB15 2 1 0 0.119 ND
DB15 220 0.104 ND
C-5
-------
TABLE C-6. SWWARY OF PCB RESULTS (in ng/L) FOR HATER SAMPLES
COLLECTED OURIKG DUMPING EVENTS, MARCH 1988 106-MILE SITE
SURVEY.
PCB
I some r
Cl3(28)
CU(52)
CU(44)
Cl4(66)
C15(101)
Cl6(153)
C16(138)
Cl6(128)
Cl7(180)
Cl7(170)
Total, dissolved
Total, participate
DB-13a
Rep. 1
5 B
0.272
0,027
0.770
0.119
1.19
-
Sample and
DB-13a DB-13*>
Rep. 2 Rep. 1
5 in 5 o
U224
0.866
1.069
0.101
0.075 0.377
0.523
0.075
4.16
Location
DB-13*>
Rep. 2
5 n
0.682
0.490
0.652
0.067
0.303
0.386
2.58
DB-14
Rep. 1
4 •
0.140
0.208
0.239
0.194
0.78
—
DB-14
Rep. 2
4 B
0.169
0.141
0.152
0.46
—
^Dissolved fraction of this sample.
bparticulate fraction of this sample.
C-6
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