FINAL REPORT
NEARFIELD MONITORING OF SLUDGE
PLUMES AT THE 106-MILE DEEPWATER
MUNICIPAL SLUDGE SITE:
RESULTS OF A SURVEY CONDUCTED
AUGUST 31 THROUGH SEPTEMBER 5, 1987
June 17, 1988
U.S. ENVIRONMENTAL PROTECTION AGENCY
Office of Marine and Estuarine Protection
Washington, DC
Prepared Under Contract No. 68-03-3319
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EXECUTIVE SUMMARY
The U.S. Environmental Protection Agency (EPA) under the Marlw
Protection, Research, and Sanctuaries Act of 1972 (MPRSA .PL 92-53^ , s
monitoring the 106-Mile Oeepwater Municipal Sludge Site J^-Mile Site). ne
objective of the 106-Mile Site monitoring program is to ensure that P^'ons
Effects.
This report presents the results from nearfield fate studies conducted at
arsa
to guide monitoring activities to assess short-term biological effects of
sludge disposal .
The 106-Mile Site monitoring plan presents several M>Jthe«s 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 are below the
permitted LPC and WQC outside the site at all times.
Results from the survey indicated that sludge plumes can be
transported outside the site before all constituents are diluted to
levels below WQC.
H«4- Concentrations of sludge and sludge constituents are bellow the
° pitted LPC and WQC values within the site 4 h after disposal.
Although the conditions at the site during the survey jere
dispersive, measured concentrations of two sludge co nstitu ejts
copper and lead, exceeded water quality criteria 4 h after disposal
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H05: Pathogen levels do not exceed ambient levels 4 h after disposal.
Concentrations of Clostridium perfrinqens. a microbial tracer,
exceeded ambient levels after 4 h in all sludge plumes monitored
during the survey.
Impact Assessment
H06: Sludge particles do not settle in significant quantities beneath the
seasonal pycnocline or to the 50-m depth at any time, within the site
boundaries or in an area adjacent to the site.
Sludge penetration below 20 m was not observed at any time during
the survey. Because a strong current "jet" occurred within the
pycnocline throughout the survey, sludge may have been transported
quickly from the survey area, precluding observations of settling.
Throughout the region, vertical profiles of natural turbidity
exhibited a subsurface maximum situated within the seasonal
pycnocline. This suggests that surface-dumped particulate matter may
accumulate within the seasonal pycnocline during summer'and coexist
with natural planktonic species.
H07: The concentration of sludge constituents is not detectable in the
site one day after disposal.
Although sludge plumes were not tracked for longer than 9 h after
disposal, calculations of dispersion indicated that all measured
sludge constituents would reach ambient levels within 1 day.
Ho8: The concentration of sludge constituents at the site boundary or in
the area adjacent to the site is not detectable one day after
disposal.
Calculations indicated that concentrations of sludge constituents
would be diluted to ambient levels within 1 day for all plumes
monitored.
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.
Any depression of oxygen levels in sludge plumes was minor. pH was
not monitored during the survey.
Results of the survey have provided the first complete assessment of
sludge plume behavior and transport under summer conditions. Many of the
measurements will be repeated during the winter, when vertical dispersion is
expected to be much greater than in the summer. The measurements will also be
repeated in the summer, so that we can develop an understanding of variability
of measurements of plume behavior. These results will also be used to plan
acoropnate measurements of short-term effects of sludge dumping and will ouide
5 ans for assessing fe -field fate of sludge constituents.
i i
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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 Water Column Profiling «3-l
3.1.2 Current Measurements 3-4
3.1.3 Aerial Photography «3-6
3 2 WATER QUALITY SAMPLE COLLECTION . . . .3-7
33 ENDANGERED SPECIES OBSERVATIONS . . .3-8
3*.4 ANALYTICAL METHODS -3-8
3.4.1 Trace Metals -3-8
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
3.4.1.5 Selenium and Arsenic ..3-11
3.4.2 Organic Compounds ?~H
3.4.3 Total Suspended Solids (TSS). . 3-11
3.4.4 Clostridium perfrinqens. 3-11
4.0 RESULTS AND DISCUSSION 4~1
4.1 OCEANOGRAPHIC CONDITIONS . . . .4-1
4.1.1 Water Mass Characteristics .4-1
4.1.1.1 CTD Transect to the 106-Mile Site .4-2
4/1.1.2 Satellite Thermal Imagery 4-5
4.1.1.3 Hydrographic Conditions at the Site .4-5
4.1.2 near-Surface Currents -4-7
4.1.2.1 XCP Current Profile Results .4-8
4.1.2.2 Near-Surface Drifter Results 4-11
4 2 BACKGROUHD WATER QUALITY 4-13
4*.3 BARGE RECORDS - J-J°
4.4 SLUDGE PU1ME BEHAVIOR *-20
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TABLE OF CONTENTS (Continued)
Page
4.4.1 Lateral and Vertical Spreading 4-20
4.4.1.1 Lateral Spreading. ...-..' 4-20
4.4.1.2 Vertical Spreading 4-25
4.4.2 Sludge Dilution and Transport 4-28
4.4.2.1 Dilution Based on Plume Volume 4-28
4.4.2.2 Dilution Based on Transmissometry Data . . . 4-29
4.4.2.3 Dilution Based on TSS Data . 4-33
4.4.2.4 Dilution Based on Chemical Tracer Data . . . 4-35
4.4.2.5 Plume Transport 4-41
4.5 HATER QUALITY MEASUREMENTS 4-45
4.5.1 Comparison to Water Quality Criteria 4-46
4.5.2 Dissolved Oxygen 4-48
4.5.3 Clostridium perfrinqens 4-50
4.6 OBSERVATIONS OF CETACEANS AND MARINE TURTLES 4-53
5.0 CONCLUSIONS . . 5-1
5.1 DISCUSSION OF NULL HYPOTHESES 5-1
5.2 EVALUATION OF MEASUREMENT TECHNIQUES. . :. 5-3
6.0 REFERENCES 6-1
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TflRI F OF CONTENTS
(Continued)
TST OF TABLES
Page
Table 2-1. Elements and Compounds for Which There Are Marine Water _
Quality Criteria ........ ............... *
2-4
Table 2-2. Monitoring Activities ........... ..........
Table 2-3 Barges That Dumped Municipal Sewage Sludge at the 106-Mile
Table i 6. t*arg ^.^ the Survey Operations From August 31 Through
September 4, 1987 ................. ...... I**1"0
Table 3-1. Measurement Specifications for CTD Sensors. . ......... -3-3
Table 3-2. Objectives for Analytical Measurements of Water Samples .... .3-9
Table 4-1. Background Water Quality Measurements in Seawater at the _
106-Mile Site, September 1-4, 1987 ............ ... .4 is
106
4-2 Summary of Dumping Information for Barges Dumping
42. Sunmry y Site From
August 31 Through September 4, 1987
Table 4-3
Table 4 .i.
Suspended Solids in Sludge Plumes and Estimates of
at the 106-Mile Site . .
Table 4-4 Total Suspended Solids in Sludge Plumes at the 106-Mile
Site Monitored After Dumping. ...
Table 4-5. Estimates of Dilution at T=0 h and T=4.3 h Based on Metal
Tracer Concentrations
4-18
,4-34
4-37
4-39
Table 4-6. Comparison of Metal Measurements in Sludge Plumes DB-2 and
SS WSSii ^&Z&£^ ^* 4-47
Table 4.7. J^4*j^ !
Non-Compliance Based on Mean Contaminant Concentrations
in Sludges From 19 Sewaae Treatment Plants in the New
York Metropolitan Area (Santoro and Fikslin, 1987), and
Mean Dispersion Rates (From Metal Tracer Data, Sludge
Plume 'OB-3)
Table 4-8. Concentrations of C. perfrinqens in the Sludge Plumes
at T=0 and Between 4 and 7 h After Disposal. (Results
are Based on the Maximum Observed in the Set ot
Replicate Samples for the Sample Period).
4-49
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LIST OF APPENDICES
Appendix A. Data Quality Assessments for Analytical Measurements ...... A-l
Appendix B. CTD Transect to the 106-Mile Site and
Water Masses During Plume-Tracking Surveys ........... B-l
Appendix C. Background Data ........................ c_j
Appendix D. Summary of Laboratory Analyses For Dumping Events DB-1
DB-2, and DB-3, 106-Mile Site, September 1987 ....!... .D-l
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TABLE OF CONTENTS
"(Continued)
Paqe
LIST OF FIGURES
Figure 1-1. Location of the 106-Mile Deepwater Sewage Sludge Site .... .1-2
Figure 3-1. Schematic Diagram of Shipboard Data Acquisition System 3-2
Figure 4-1. Vertical Transect of Hydrographic Properties Along Eastbound^ ^
CTD Transect
Figure 4-2. Composite of Hydrographic Profile Results from Stations ^ ^
1, 4, and 5
^_._ ~* u,+^ M«C Boundaries onq ^ ^ ^ ^g
,_J, Current Direction,
No. 6 on September 4, 1987 . . .4-9
. . .4-10
Figure 4-6. Composite of Current and Water Temperature Profiles Obtained
ngure * u ^< ^^ Launched During the Four Plume Surveys . i ;i«
Figure 4-7. Summary of Near-Surface Drifter Trajectories from Plume ^
Surveys DB-1, DB-2. and DB-3
ngur.,4-8. Barge Dumping ^^gc,^ tjj Four Princi^
(DZ^l) thafoumped on the Day Prior to Survey DB-1. ..... 4-19
Figure 4-9. Results from Analyses of Aerial Photography for j
9 Plume Surveys DB-1 through DB-3
Figure 4-10. Analysis of Plume Width for Plumes DB-2 and DB-4. . 4-23
Figure 4-11. Composite of Vertical Turbidity (Beam Attenuation) Profiles
made Within Plume DB-3 '
Events DB-1 and DB-4
Figure 4-13, TSS Concentration^and^TSS^oad^Ca cuj^e^ ^ ^ ?^^ ^ ^ ^ 4_32
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TABLE OF CONTENTS
(Continued)
LIST OF FIGURES
(Continued)
Fiaure 4-14A. Total Suspended Solids Concentrations Monitored During
Dumping Event DB-1 (Sludge From Wards Island Sewage
Treatment Plan, New York, NY) 4-36
Fiaure 4-14B. Total Suspended Solids Concentrations Monitored During
Dumping Event DB-3 (Sludge From Port Richmond Sewage
Treatment Plant, New York, NY) 4-36
Fiaure 4-15. Copper,- Lead, and Zinc Concentrations Monitored During
Dumping Event DB-3 (September 3, 1987) 4-40
Figure 4-16. Diagnostic Tracer Ratios for Sludge Plumes DB-2 (Sludge
From Wards Island Sewage Treatment Plant, New York City,
NY) and DB-3 (Sludge From Port Richmond Sewage Treatment
Plant, New York City, NY) 4-42
Figure 4-17. Summary of Plume Advection for Plumes DB-1 and DB-2 4-43
Figure 4-18. Summary of Plume Advection for Plumes DB-3 and DB-4 4-44
Fiaure 4-19. Variations in Water Properties Along a Transect of Plume
DB-4 that Was made 55 Minutes After Discharge from the
Barge. Reductions in Salinity, Sigma-t, and Oxygen
Correspond With High Turbidity and (Beam Attenuation)
Within the Plume 4"51
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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) ( EPA , 1987a). 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-
Term 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 di.sposal 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 concentration
1-1
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106Mil* D««pwattr
Municipal SJudg* Sit*
T5URE 1-1. LOCATION OF THE 106-MILE DEEPWATER MUNICIPAL SLUDGE SITE.
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of the sludge not exceed a factor of 0.01 tlme^.Ct^Cente^^b"ne°Wn *" "' :
potent,, for impacts .thin
the site. Monitoring behavior and movement of sludge ,-ediately after
posa! is necessary to eonflr. assumptions regarding di.persion and , u on
that will be used in issuing permits. This information will also be used to
gufde litoring activities to assess short-term biological effects of sludge
ile Site monitoring plan presents the following hypotheses
related to neat-field. fate of. sludge plumes:
it Compliance
: --rations
^e.nstitue.s^ide the
H05: Pathogen leve!s do not exceed ambient levels 4 h after disposal
Assessment
the site one day after disposal
1-3
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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 , 19925):
Permit 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, chemical
and microbiological parameters are being made to determine
whether concentrations of sludge constituents meet permit
conditions and are at background levels within one 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 one 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 , 1988 ). Visual
observations and measurements of sludge tracers (total suspended solids and
1-4
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spores of the microbe Clostridium perfrinqens) indicated that sludge pTu.es
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-tern impacts from disposing sludge at the
then developed a strategy for comprehensive assessment of nearfield,
short-term fate of sludge constituents ( EPA '. 1987.) . 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 a plume-tracking exercise
at the site:
Permit Compliance
within 4 h after doping and outside the site boundaries
times.
all
Impact Assessment
Determination of the dilution of sludge in seawater immediately
upoHumping and during the first hour after dumping.
Determination of the short-term effects of sludge on the dissolved
oxygen levels at the site.
surface
Determination of the extent of horizontal dispersion of the plume.
Determination of the extent of vertical dispersion of the dissolved
and parti cul ate components of the plume.
. Determination of whether sludge constituents settle below the summer
pycnocline.
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This information was obtained through repeated sampling of sludge plumes
during a survey at the 106-Mile Site in September 1987. Results of that survey
are presented in this report. Chapter 2 presents the strategy for making
measurements of sludge constituents and tracers of the plume. 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 methods used to track sludge plumes and an
assessment of behavior and transport of plumes in terms of the null hypotheses
are presented in Chapter 5.
Results of the survey have provided the first complete assessment of
sludge plume behavior and transport under summer conditions. Many of the
measurements will be repeated during the winter, when vertical dispersion is
expected to be much greater than in the summer. The measurements will also be
repeated in the summer, so that we can develop an understanding of the
variability of measurements of plume behavior. These results will also be used
to plan appropriate measurements of short-term effects of sludge dumping and
will guide plans for assessing farfield fate of sludge constituents.
1-6
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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 setting of sewage
sludge as sludge plumes are transported towards and beyond the sue boundary,
and (Z) determine whether water quality requirements that will be included ,n
permits for dumping at the site are being met during ongoing disposal
operations. Because this survey was the first field appHca^on of P^
technical guidance for plume-tracking activities to be conducted as part of the
106-Mile Site monitoring program, an additional objective was to test equipment
and protocols for future plume-tracking activities that may be conducted by EPA
or by permittees. .
EPA strategy to accomplish these objectives involved conducting the
following methods in the survey:
' identification and tracking of a sludge plume with dye and \
surface and subsurface drogues.
and a contracted aircraft.
Acauisition of in situ transmissometry and acoustics data and
shipboard Sv/fluSrescence data to monitor the movement and
dispersion of the plume.
p «
sludge components and dilution of these components.
Collection of samples for analysis °^h
have marine water quality criteria (WQC,
Acquisition of satellite-derived ocean frontal analyses,
the survey.
Acquisition of real-time navigation data to support plume-
tracking activities.
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TABLE 2-1. ELEMENTS AND COMPOUNDS FOR WHICH THERE ARE MARINE
WATER QUALITY CRITERIA&
Inorganic Elements
Organic Compounds
Arsenic
Cadmium
Chromium (hexavalent)
Copper
Cyanide
Lead
Mercury
Nickel
Selenium
Silver
Zinc
Aldrin/Dieldrin
Chlordane
DDT and Metabolites
Endosulfan
Endrin
Heptachlor
PCBs
Toxaphene
samples on this work assignment were analyzed for total chromium instead
of hexavalent chromium. Cyanide'was not analyzed.
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Observations of endangered species of ce taceans |Hne
Site.
The primary method for tracking sludge plumes was use of
transmissometry, which measured turbidity resulting from high levels of total
suspended solids in sludge. Both horizontal and vertical transmissometry
profiles were used to monitor nearfield fate of disposed sludge in a marked
volume (by surface drifters and Rhodamine dye) of sludge plume. Horizontal
profiling techniques provided data on the horizontal and vertical dispersion of
sludge, and resulted in relatively more data on lateral spreading. Vertical
profiling resulted in data on vertical dispersion. Both profiling techniques
were supported with the collection of samples for chemical and microbiological
tracers. However, relatively more samples were collected during vertical
profiling. Surveying operations were also supported with aerial .
photoreconnaissance provided by Aero-Marine Surveys, Inc. The aerial
photoreconnaissance provided information on lateral plume spreading and plume
orientation. A summary of horizontal and vertical profiling activities is
presented in Table 2-2. '
The survey was extremely successful in achieving objectives and
performing all survey activities. Several CTD profiles were made during^the
transit to the site to characterize the water masses at the site and vicinity.
At the site before surveying operations began, all equipment and procedures
were tested and samples were collected for background water quality. The
survey monitored four sludge plumes, identified as DB-1 through 08-4, on
September 1 through 4, 1987 (Table 2-3). The sludge plumes were monitored from
3 5 to 9 3 h each, allowing EPA to gather information on short-term and
nearfield physical, chemical, and microbiological characteristics of sludge
dumped at the site. A fifth sludge plume (DZ-1) was monitored for a short
period of time on August 31, 1987. Data from DZ-1 are incomplete and do not
contribute significantly to this report.
A complete description of the survey is presented in the initial survey
report and in the site condition report for the survey ( EPA , 1987d and
EPA , 1987e).
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Activity
TABLE 2-2. MONITORING ACTIVITIES
Subactivity
Transect CTD Profiles
Shakedown Exercises
Vertical Profiling
Horizontal Profiling
None
Use of all oceanographic gear to track dye.
Activities include horizontal and vertical
profiling with in situ and pumping equipment
and collection of water samples for WQC contam-
inants.
CTD/transmissometer and acoustic vertical pro-
filing; pumping water from surface to 50 m,
collection of pumped samples for tracers, WQC
contaminants, TSS, and C. perfringens; XCP
profiling.
Towed fish with CTD/transmissometer, transmis-
someter; pumping water from surface to 50 m
(fluorometry measurements), collection of
pumped samples for tracers, WQC contaminants,
TSS, and C. perfrinqens; XCP profiling.
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Buster
Bouchard
Sea
Trader II
Spring
Creek
1340 9/1 to
0335 9/2
1642 9/2 to
1950 9/1
1010 9/2 to
1400 9/2
1055 9/3 to
1535 9/3
26th Ward, New York City
Graves End Bay, Brooklyn
Ward's Island, New York City
Wards Island, New York City.
Port Richmond, New York City
2-5
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3.0 SAMPLE COLLECTION AND ANALYSIS METHODS
3.1 ' PHYSICAL OCEANOGRAPHY MEASUREMENTS
Physical oceanographic data were acquired during the survey by vertical
and horizontal profiling of the water column, vertical profiling of surface
currents, and dep' Dying near-surface drifters. Aerial reconnaissance and
photography were also employed to document the behavior of the plume.
3.1.1 Water Column Profiling
Vertical and horizontal water column profiling was performed with a Sea-
Bird Electronics conductivity-temperature-depth (CTD) system interfaced to an
IBM-compatible personal computer. A Sea-Bird Electronics dissolved oxygen
sensor and a Sea Tech 25-cm 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 transmits digital information to a deck control
unit via a Kevlar electromechanical (E/M) profiling cable. The CTD deck
control unit passes the raw CTD data to the computer of the shipboard data
acquisition system for real-time display and data storage. A Northstar 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.
For all profiling operations, the stainless steel support frame of the
CTD underwater unit was attached to the lower side of a 3-foot (wingspan)
Endeco V-Fin towed depressor. For horizontal profiling (towing) the E/M cable
was attached-to the top of the V-Fin such that the CTD was towed horizontally
with sensors pointing forward to ensure undisturbed flow past the sensors. Fo
v-tlcal profiling the mechanical termination of the E/M cable was attached to
V-e -op end of the CTD support frame, with the V-Fin still attached to the CTD
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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
3-2
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TABLE 3-1. MEASUREMENT SPECIFICATIONS FOR CTD SENSORS
Parameter
Depth
Temperature
Salinity
Oxygen
Light Transmission
Range
0 to 3000
-5 to 35°C
0 to 40 ppt
0 to 15 mL/L
0 to 100 %
Accuracy
+60 cm
+0.004°C
±0.005 ppt
+0.1 mL/L
+0.5 %
Resolution
12 cm
0.0003°C
0.0005 ppt
0.01 mL/L
0.01 %
Sampling rate: 24 samples per second (averaged to 4 samples per
Vertical resolution during profiling: ~40 cm
Horizontal resolution during towing: -40 cm at 3-knot ship speed
3-3
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frame. Leaving the V-Fin attached to the CTD allowed faster CTD lowering rates
due to the added mass of the V-Fin.
Following the survey, binary data files of the digital CTD data were
returned to the laboratory for processing and review. The binary files of raw
data are stored on the hard disk of Battelle's IBM-compatible physical
oceanographic data processing computer system. Backup copies of the raw CTD
data are also stored on 5-1/4 inch floppy disks and archived. Hard copies of
printouts and graphic plots of CTD data that were generated in real time during
the cruise are also archived with the backup disks of raw data.
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 units:
depth (m), temperature (*C), salinity (ppt), oxygen (mL/L), and
light transmission (% 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.
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
sr'croromputer, 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
. 3-4
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transmuted 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 which would
affect plume advection and tracking operations. XCP data are stored on floppy
disks for easy access from analysis programs.
A comparison of current vectors obtained from an XCP and a 2-h trajectory
of a drogue situated at 30 m (plume survey DB-2) indicated that current speeds
agreed to within a few centimeters per second and current directions agreed to
+5 degrees. This comparison suggested that both current measurement techniques
worked remarkably well, and that the XCP was a good indicator of absolute
currents in the upper water column. ;
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 plume
tracking operation/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 30 m,
was deployed alongside a shallow drifter for one of the plume operations to
observe the currents beneath the seasonal pycnocline. Because the sludge
plumes were apparently confined to the upper 20 m of the water column, there -
was no operational need for tracking water beneath the pycnocline, and the use
of "deep" drifters was terminated.
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, 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, *
file of positions and times has been archived to facilitate analyses of
trajectories and current vectors.
3-5 . ''''
-------
3.1.3 Aerial Photography
Reconnaissance by aerial photography was provided for three of the four
plume tracking events. Using twin Hasselblad cameras mounted in the base of a
twin-engine survey plane, a total of 169 photographic images were acquired
during 9 h of photoreconnaissance at the 106-Mile Site. The majority of these
images were taken directly over the survey vessel and dye patch in order that
the images could be used to determine the rate of spreading of the sludge
plume. To facilitate quantitative analyses, a computerized data file was
established for management of the following information for each photograph:
time, date, aircraft Loran-C position, aircraft elevation, and aircraft
heading.
Of the 169 photographic images obtained, a subset of 55 images were
selected for detailed analysis, and a~10 x 10-1n color print was made of each
image. The selection of images was based upon (1) the requirement that the dye
patch and/or survey vessel be within the field of view; (2) the need for
distinct surface boundaries of the sludge plume; and (3) the need for a
reasonable time series of images throughout the reconnaissance survey.
Quantitative analyses of the photographic prints consisted primarily of
measurements of plume width and plume heading. Accurate measurements of plume
width were obtained because the elevation of the aircraft was recorded with
each image and, therefore, a distance scale could easily be made to convert
from millimeters on the photographic print to meters across the plume in full
scale. Having the OSV Anderson in the field of view for most of the images
provided a useful calibration check on the measurements of plume width because
the vessel's length could be measured on the photograph and compared with the
vessel's actual length. We estimate that the error in distance measurements
from the aerial photographs is on the order of ±5 m. This error is
significantly less than the actual small-scale variability in plume width that
is observed as the plumes spread behind the barges.
Thirty minutes after discharge, most of the plumes exhibited a noticeable
sinuous behaviour with surface filaments extending downwind, which made it
difficult to.accurately determine the true width of the plume. Care was taken
to measure plume width at the same position (in the vicinity of the dye patch)
3-6
-------
in order to minimize interpretation errors, but after about one hour
uncertainties in plume width were on the order ±25 m and useful, quant,tat,ve
results could no longer be obtained.
Analyses of plume heading were performed using the aircraft heading the
geographic orientation of the photographic image) and the or1ent.t,on of the
pluL as measured on the photographic image. The combined error in the
determination of plume heading is estimated to be ±5 degrees.
3.2
Seawater sables for analysis of trace metals, organics. total suspended.
solids (TSS), and C. oerfrinoens were collected from several depths «th two
ing sysL. One system, designed for Election of surface -te-amples,
consisted of a 10- Teflon tube connected to either a polypropylene bellows
metering pump or a stainless steel pump. Samples for metals, TSS, and
C. serfrinaens analysis were obtained from the polypropylene pump; the _
pump was used to collect water samples for analysis of -
tase pump w
chemicals. A second system for collecting subsurface water samp m oy ^77
. of Teflon tubing housed on a stainless steel hose w,nch. The inlet for the.
tube was connected to the CTD system to deploy it to the desired depth.
Subsurface water was pumped through either the bellows pump or, when samples
for organics were collected, to a stainless steel centrifugal pump.
unfiltered samples collected for trace metals analysis were preserved
with high purity nitric acid (1 mL/L or 5 mL/L for mercury samples). Samples
or TSS were processed on board the survey vessel by filtering seawater samp es
through 0.4-^, Nuclepore filters. The filters were precleaned and Prewe,9hed
to within 1 «. The particulate sample was rinsed three times with 30 m of
deionized water adjusted to pH 8.0 with NH4OH to remove res,dual sea salts.
Filters were labeled and stored for shipment to the laboratory.
Samples for organic contaminant analysis were collected in 150-1 sta,n ess
steel tanks and extracted with dichloromethane, The dichloromethane extracts
were stored for shipment to the laboratory.
3-7
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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 OSV Anderson. These observations were recorded along
predetermined survey paths in 15-min periods, where each period represented a
transect.
The data were recorded into two major categorieslocation/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 species group (mammal, turtle), 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 methods used to verify the
accuracy and precision of these methods are presented in the Work/Quality
Assurance project plan for this work assignment. 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.
3.4.1 Trace Metals
Methods for the extraction and analysis of trace metals varied for some
elements and are summarized below.
3-8
-------
TABLE 3-2. OBJECTIVES FOR ANALYTICAL MEASUREMENTS OF WATER SAMPLES
parameters
^=I^^raffim^=^=j=«-»
Detection Percent Percent
Units Liarits Accuracy Precision
Method
Seawater Oroanics
PCB congeners,
pesticides
SeawaterMetals
.001
50
100
Ag, Cd, Zn
Cr, Pb, Cu
Fe
Hg
As
Se
Seawater TSS
^g 1 L .015
pg/L .030
ng/l -050
(ig/L .0005
pg/L -02
pg/LL .7
mg/L .01
20
20
20
20
20
20
20
15
15
15
15
15
15
15
Solvent extraction,
GC-ECDa
Chelation extraction,
GFAAa
Chelation-extraction,
GFAAa
Chelation-extraction,
GFAAa
Gold trap. Hg
analyzer^
Hydride, CVAAS
Hydride, CVAAS
Filtration, gravime-
tric determination0
a EPA , 1987b.
b EPA , 1987f.
3-9
-------
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 ammoniurn-1-pyrrolidine dithiocarbamate diethyl ammonium
diethyldithiocarbamate (APDC-DDDC) and Freon (Danielsson et al., 1982). Each
sample was extracted three times with 5-mL 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 Zeeman 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 NH40H.
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
stannous chloride in a closed vessel. The sample was purged with nitrogen and
the resulting elemental mercury was concentrated on gold-coated 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.
3-10
-------
3.4.1.5 Selenium 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.
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).
3.4.4 Clostridium perfrinoens
Enumeration of C. perfrlnqens in seawater was performed according to the
methods of Bisson and.Cabelli (1979). C. oerfrinqens-spores were collected by
filtering 0.1-, 0.5-, and 1-L aliquots of seawater through 0.4-Atm polycar-
3-11 :
-------
bonate filters immediately after collection. The filters were cultured
anaerobically on modified C. perfrinoens (m-CP) medium. Confirmation was
obtained by exposing the incubated plates to ammonium hydroxide vapors which
turn C. oerfrinaens colonies a magenta color. The bacteria were quantified as
number of colonies per 100 ml of filtered seawater.
3-12
-------
4.0 RESULTS AND DISCUSSION
Results of the September 1987 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 Water Mass Characteristics
The hydrographic 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
conductivity/temperature depth (CTD) profiling system described in Section 3.
This type of data set can be utilized and presented in a variety of ways to
provide information relevant to the objectives of the survey. Examples of such
hydrographic 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 of 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.
4-1
-------
Oceanographic characterization of the site to allow
comparisons with past and future surveys, and which can
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 eastbound transit to the 106-Mile Site on August 31, 1987, a
series of seven CTD profiles were made along a line extending from the edge
of the continental shelf, through the northern end of the 106-Mile Site, to a
position roughly 8 miles northeast of the site (see station positions in
Appendix B). The primary objectives of this CTD transect were to locate the
position of the shelf water/slope water front (west of the 106-Mile Site),
and determine whether a warm-core Gulf Stream eddy was situated near the
eastern boundary of the site, as suspected from interpretations of satellite
thermal imagery. A detailed discussion of the hydrographic conditions along
this transect is given in Appendix B; a summary of the most pertinent results
is provided below.
Hydrographic conditions within the upper 150 m of the water
column along the transect were typical for summer conditions, as
deduced by comparison with past studies along the u.b. tast
Coast.
A thin (~20 m) layer of relatively fresh shelf water extended
eastward from the continental shelf such that the shelf
water/slope water boundary lies 25 nmi to the west of the 106-
Mile Site.
» Despite extensive temperature/salinity variability in the upper
water column, vertical profiles of density were very similar at
all stations (see Figure 4-1). Beneath a surface mixed layer, a
sharp seasonal pycnocline extended from roughly 20 to 40 m along
the entire transect that included the northern portion of the
106-Mile Site.
» Throughout the region, vertical profiles of natural turbidity
exhibited a subsurface maximum situated within the seasonal
pycnocline (see beam attenuation profiles in Figure 4-2).
4-2
-------
TEMPERATURE (C)
-3 .4. .5
1 50
72°56-W
Longitude
71° 56'W
SALINITY (PPT)
1 5O
72°56'W
Longitude
7 1 ° SB'W
o i*
5 SO
SIGMA T
. .4.
1 5O
72°56'W
Longitude
7 1 ° 56'W
FIGURE 4-1. VERTICAL TRANSECT OF HYDROGRAPHIC PROPERTIES ALONG EASTBOUND
CTD TRANSECT (SEE APPENDIX B FOR STATION LOCATIONS);
TEMPERATURE (UPPER); SALINITY (MIDDLE); SIGMA-T (LOWER).
4-3
-------
SIGMA-T
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BEAM ATTENUATION tl/m)
0.4 0.6 0.8
OXYGEN (al/1)
1.0
200-
E 4-2.
COMPOSITE OF HYDROGRAPHIC PROFILE RESULTS FROM STATIONS 1, 4
AND 5: SIGHA-T PROFILES (UPPER); BEAM ATTENUATION PROFILES
(MIDDLE); OXYGEN (LOWER).
4-4
-------
Dissolved oxygen profiles exhibited maximum values exceeding 6
mL/L within the seasonal pycnocline (see F'9ure 4-2); percent
saturation values within this maximum reached 110%. These hign
natural oxygen levels are associated with high biological
productivity and relatively high natural turbidity within the
pycnocline.
4.1.1.2 Satellite Thermal Imagery
As discussed in the site condition report ( EPA , 1987e), the Ocean
Frontal Analyses of the U.S. East Coast, prepared by the Marine
Climatological Investigation of the National Marine Fisheries Service in
Narragansett, Rhode Island, frontal analyses are marginally useful for
locating ocean thermal features during summer months. 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 Gulf Stream meanders, but during summer,
surface warming greatly reduces the thermal contrast between these water
masses.
During a 3-week period prior to the survey, a warm-core eddy named "87-
E» approached the 106-Mile Site from the northeast, but satellite tracking of
this feature became increasingly difficult because of (1) the weak surface
thermal expression of the eddy, and (2) extensive cloud cover which greatly
reduced the number o' useful satellite images. Figure 4-3 presents a
simplified version of the ocean frontal analysis for August 31, 1987, the
first day of the survey. This analysis suggests that eddy "87-E" was
situated only 50 km to the east of the site, such that currents at the site
would be directed toward the northeast, Hydrographic and current data
presented elsewhere in this report illustrate that water properties and near-
surface dynamics at the site were being affected by the outer edges of eddy
"87-E" during the 5-day survey.
4.1.1.3 Hydrographic Conditions at the Site
Although the majority of the CTD profiles during the survey were made
within sludge plumes, analyses of data from stations outside of the plumes
4-5
-------
40 N
35 N
73 K
70 W
65 W
FIGURE 4-3. SCHEMATIC REPRESENTATION OF WATER MASS BOUNDARIES ALONG THE
U.S. EAST COAST ON SEPTEMBER 1, 1987, AS DERIVED FROM
SATELLITE THERMAL IMAGERY. WARM-CORE EDDIES ARE LABELED "87-
E",' "87-C", AND "87-F".
4-6
-------
illustrate the background hydrographic conditions of the receiving water at
the site:
relatively salfte water of GuUStream origin from the
periphery of warm-core eddy 87-E.
properties
Dissolved oxygen concentrations were consistently high (>6 mL/L,
and ~110% saturation) within the seasonal pyqnocline.
4.1.2 Near-Surface Currents
Near-surface current observations during the survey were obtained from
(1) expendable current profilers (XCPs), and (2) tracking of surface markers .
that were attached to subsurface drogues. The XCPs were the primary current
.easurement tool, as they provided accurate, high-resolution profile, of _
current shear from the surface to depths of 1500 m. Because the XCPs worked
well only one or two drifters were deployed during each plume tracking
survey/ 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 survey. !
The current profile data have been analyzed with the objective of
resolving the local current regime at the time of the survey. As .will be ,
shown below, the field measurements were adequate for resolving .
. The profile of current speed and direction over the upper 1500 m of
the water column;
The vertical structure of an intense current "jet" situated within the
seasonal pycnocline;
The rate at which sludge plumes were advected out of the site. :
4-7
-------
4.1.2.1 XCP Current Profile Results
All six of the expendable current profiler (XCP) probes that were
launched during the survey provided good-quality, high-resolution current data
from the surface to depths of approximately 1500 m. Due to an inherent design
limitation, XCPs generally do not provide good quality data within the upper 5
to 7 m of the water column. Therefore, the results presented below are based
upon current profiles that begin at a depth of 7 m. Note also that the high-
resolution data have been vertically averaged to provide current observations
at 3-m intervals throughout the profile range.
Figure 4-4 presents vertical profiles of current speed, current
direction, and water temperature that were acquired during XCP profile 6,
which was launched at the northern boundary of the site on the final day of
the survey, September 4, 1987. This profile is representative of the current
conditions observed at the site throughout the survey. Figure 4-4 illustrates
that current speeds were weak (<10 cm/s) and relatively constant below 600 m
(the base of the main thermocline), but speeds above that level generally
increased toward the surface. The highest current speeds (~0.9 kn) were
observed above 50 mt apparently within the strong seasonal thermocline that
ranged from roughly 12 to 22°C. Current directions were eastward above 300 m,
and northeastward below that level.
To illustrate the variability in upper ocean currents during the survey,
Figure 4-5 presents a composite of current profile data obtained from the four
XCPs (3 through 6) launched during the four plume tracking events (DB-1
through DB-4). This composite of current vectors presents data from six depth
levels to allow detailed comparison between individual profiles. Each current
vector illustrates the direction of flow using the standard compass
convention, with north pointing upward. The length of each vector is
proportional to current speed with a scale given at the bottom of the figure.
Note, that the current vectors at 5 m are derived from drifter trajectories
because the XCPs do not provide good quality data at the surface.
From the composite of current vectors presented in Figure 4-5, the
following characteristics of the local current regime emerge:
4-8
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OBSERVED CURRENT VECTORS
DB-l DB-2 DB-3 DB-4
5n
Maxlnun
Current
( 1 3- 16n)
50-250n
250-500n
500-1OOOn
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:!GURE 4-5.
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ARE REPRESENTED BY AN ARROW POINTING UPWARD.
4-10
-------
For all profiles, the maximum current speed was observed at 13 to
16 m; current directions within this "jet" were highly variable,
but the easterly component was pronounced.
Currents at 5 m were much less intense than currents within the
"jet" located only 10 m deeper.
Currents between 50 and 250 m were very constant and directed
toward the east.
Currents at lower levels were weak and more variable in direction,
but most had an eastward component.
The most striking feature evident from the current profile data is the
intense current "jet" situated at roughly 15 m. These intense currents were
apparently situated within the seasonal pycnocline, but further inspection is
required to demonstrate this vertical correspondence. Figure 4-6 presents
current and temperature profile data from the upper 100 m of the four XCPs
presented in Figure 4-5. All four profiles demonstrate maximum current speeds
within a depth range from 15 to 20 m, which coincides with the near-surface
thermocline (and pycnocline). This "jet" was most intense during the first two
days of the survey, possibly because of the sharp (8° to 20°C) thermocline that
was observed at that time; warmer (12°C) water displaced the temperature
minimum during the final two days of the survey, causing a weaker seasonal .
thermocline. It is unknown whether the "jet" was associated with the perimeter
of the warm-core eddy situated to the east of the site or if the "jet" is a
persistent feature that will be present during other seasons, or during the
summer every year. Implications of the pycnocline current "jet" with regard to
mixing and transport of sludge dumped at the 106-Mile Site are discussed later
in this report.
4.1.2.2 Near-Surface Drifter Results
Real-time current profile data from the XCPs provided valuable 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.
4-11
-------
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,
,f the wat" coiu», the drifters provided viable infon.at,on on
rr rru
. Near-surface (5-.) currents varied great!, over the 3-day period.
. currents at 30 ..were nuch stronger than 5-. currents during plume
event DB-1.
. Hear-surface currents for plujes DB-2 and DB-3 were directed
toward the east at speeds of 0.6 kn.
. The drifter results generally agreed with near-surface current
data from the XCPs.
water collected at reference sites was analyzed for water quality criteria
water, con ec total suspended solids, and C. Eerfru^
(WQC) contaminants (Table 2-1), iron, low v Clirvev
prior to or i-ediately following each plu^e-trac ,n, eve A
concentrations of «,t trace .etals were unifo^ly low in all
4-13
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4-14
-------
TABLE 4-1.
1987
.-4.
Parameter
Metals
Arsenic, total
Cadmium
Chromium, total
Copper
Lead
Mercury
Nickel
Selenium
Silver
Zinc
Organic Compounds
Aldrin
Chlordane
Dieldrin
p.p'-DDT
p,p'-DDE
a-Endosulfan
Endrin
Heptachlor
Total PCB
Toxaphene
a-BHC
7-BHC
Total Suspended Solids
r. perfrinqens
Concentration*
Range
fjto/L)
0.93-1.29
0.013-0.028
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
(no/I)
ND
ND
ND
ND
ND
ND
ND
ND
ND- 0.066
ND
ND- 9.4
ND- 2.5
(mo/I)
0.16 to 0.93C
f»/100 ml)
EPA Marine
Water Quality
Criteria
Chronic
Acute
2,
9.3
2.9
5.6
0.025
8.3
54
86
43
l.lOOb
2.9
140
2.1
75
410
2.3
95
_
4
1.9
1
8.7
2.3
3.6
3.0
0.2
1,300
90
710
130
34
37
53
10,000
210
"TWO background mples collected prior to event DB-2 are not included m the
ranqe Metals and C. perfringens levels in these two samples were elevated.
Sam^ng equipment was thought to be contaminated with sludge from DB-1.
bvalues for arsenic V and chromium VI are reported.
CHigh"t values were in the particle maximum located in the pycnocl^ne
doptpctable concentrations were found in two sets of background samples,
but~are throught to be from carryover in sampling equipment.
4-15
-------
criteria. Metals levels in background water were lower than previously
reported at the 106-Mile Site ( EPA , 1987c, EPA , 1988 ). The lower
reported concentrations are the result of improved collection and analysis
techniques required for determination of ambient open-ocean levels of these
elements.
Ambient concentrations of organic contaminants were also uniformly low.
All WQC pesticides were below detection limits. Analysis for PCB revealed no
distinct elution pattern by gas chromatography. However, a single PCB isomer
was found and quantified in some samples. Two pesticides (alpha BHC and gamma
BHC) that are not on the EPA water quality criteria list were identified in
almost all background water samples. Those compounds were also found
previously in site waters ( EPA , 1987c, EPA , 1988 ).
TSS concentrations in surface waters at the 106-Mile Site were relatively
constant, ranging between 0.18 and 0.56 mg/L during the survey. Concentrations
in the pycnocline (starting at 15-m and ending at 20-m depth) were consistently
elevated relative to those at 6-m depth. The TSS data are consistent with in
situ transmissometry, which showed a particle maximum in the pycnocline.
Several background samples collected after plume tracking was initiated
contained measurable levels of C. perfringens. However, no C. perfringens
colonies were found in the control station sampled prior to plume tracking.
Low C. perfringens counts may have resulted from contamination of sampling
equipment during plume tracking events.
4.3 BARGE RECORDS
An essential component in the analyses of sludge plume behavior is the
information contained in the Ocean Dumping Notification Forms submitted to EPA
following each dumping event. From the information given on these forms, it is
possible to determine the volume of sludge dumped, the length of the plume, the
speed of the barge, and the average rate of dumping (volume divided by elapsed
time), This information is extremely important for analyses of sludge plume
behavior because the initial size of the plume, the concentration of sludge
within the plume, and the rate of initial mixing are all highly dependent upon
the dumping characteristics of the barge.
4-16
-------
Table 4-2 presents a summary of dumping information for the barges which
used the site from August 31 through September 4, 1987. In addition to the
four plume events (DB-1 through DB-4) addressed in this report, dumping
characteristics are also given for a fifth sludge plume (DZ-1) which was dumped
on the afternoon prior to survey DB-1. Information for plume DZ-1 has been
included for comparison because the sludge volume and plume length of DZ-1 were
so much greater than the other four plumes surveyed.
Figure 4-8 graphically presents information from Table 4-2 to illustrate
significant differences between the individual dumping events. The upper panel
in Figure 4-8 presents a plot of sludge volume dumped versus barge speed for
the five dumping events. This figure illustrates a number of differences
between the various dumping events: dumping event DZ-1 had much greater sludge
volume than the other four events (DB-1 through DB-4), whereas barge speed was
the lowest of all five'barges; sludge volumes of events DB-1, DB-2 and DB-3
were nearly identical, but barge speed for DB-3 was significantly greater than
for all other barges.
Of more importance in the analysis of plume behavior are (1) the actual
sludge dumping rate, and (2) the initial concentration of sludge within the
plume. The average rate of sludge dumping can be calculated from each barge
record by dividing the total volume of sludge dumped by the time spent during
dumping. The initial concentration of sludge within the plume is related to
the amount of sludge that is dumped along the entire track (plume) length.
The volume of sludge per meter of track length can be obtained by simply
dividing "the volume of sludge by the total length of the plume.
The lower panel of Figure 4-8 presents a plot of these two calculated
quantities, dumping rate (gallons/min) and sludge volume per unit of track
length (gallons/meter), for each of the five dumping events. Dumping event
DB-1 was the only one of the five events in which sludge dumping rates exceeded
15,500 gal/min. In terms of sludge dumped per unit of track length, event DB-1
also had the highest values. In contrast, event DB-3 had the lowest value of
sludge per unit of track length, and presumably, this plume would initially
have the lowest sludge concentrations (and highest dilutions) of all plumes
surveyed. As will be shown in following sections, sludge volume per unit track
length is an important parameter affecting of plume dilution.
4-17
-------
TABLE 4-2. SUMMARY OF DUMPING INFORMATION FOR BARGES DUMPING
SEWAGE SLUDGE AT THE 106-MILE SITE FROM
AUGUST 31 THROUGH SEPTEMBER 4, 1987
Survey
Date
Tug
Barge
Sludge
Volume
(gal)
Barge
Speed
(kn)
Dumping
Time
(h)
Plume
Length
(nmi)
Average
Dumping
Rate
(gal/min)
(gal/meters)
(m3/m)
DZ-1
8/31
Buster
Bouchard
Sea
Trader
9,200,000
4.2
13.9
58.3
11,018
85
0.32
DB-1
9/1
Alice
Moran
Spring
Creek
3,291,428
5.3
3.1
16.5
17,506
108
0.41
DB-2 DB-3
9/2 9/3
Ester Kate
Moran
Tibbetts Morris
Brook Berman
3,328,831 3,342,893
5.0 7.3
3.8 4.7
19.2 34.0
14,473 11,939
94 53
0.36 0.20
DB-4
9/4
Dragon
Lady
Leo
Frank
1,309,090
5.7
1.7
9.5
13,091
74
0.28
4-18
-------
10
D
cn
LJ
O
UJ
O
O
in
8-
6-
0
0
DZ-1
DB-2
DB-3
DB-V
DB-4
2 3 45 6 7
BARGE SPEED (kts)
8
20000
E
\
o
.LJ
18000-
16000--
0 14000--
Z
D_
12000-
O
10000
0
DB-1
DB-2
DB-4
DB-3
DZ-1
25 50 75 TOO 125
GALLONS / METER OF TRACK
150
FTPIRF 4-8 BARGE DUMPING CHARACTERISTICS FOR THE FOUR PRINCIPAL PLUME
SURVEYS (DB-1 THROUGH DB-4), AS WELL AS A BARGE (DZ-1) THAT
DUMPED ON'THE DAY PRIOR TO SURVEY DB-1.
4-19
-------
4.4 SLUDGE PLUME BEHAVIOR
4.4.1 Lateral and Vertical Spreading
To determine the short-term mixing and dispersion characteristics of
sludge plumes that were dumped at the 106-Mile Site, it is first necessary to
quantify their spatial scales and the rates at which they vary. The following
sections present analyses of sludge plume width and thickness, as determined
from aerial photography and shipboard profiling with the CTD/transmissometer
system.
4.4.1.1 Lateral Spreading
Plume width data were obtained from four separate plumes, and repeated
observations within each plume allow analysis of the rate at which plumes
spread laterally. Plume width data were obtained from horizontal profiling for
two plumes (DB-2 and DB-4) and from aerial photography for three plumes (DB-1,
DB-2, and DB-3).
Figure 4-9 presents a summary of results obtained from aerial photographs
of three plumes. The upper panel presents estimates of plume width versus time
during the first 2 min following sludge dumping from the barge. The results
from plumes DB-1 and DB-3 were each obtained from a single photograph of the
sludge plume immediately behind the barge. The data were derived by (1) using
the known speed of the barge to convert from distance-behind-the-barge to
time-since-dumping, and (2) measuring the plume width (corrected for aircraft
elevation) at various distances behind the barge. This figure illustrates that
plume DB-1 was initially much wider than plume'DB-3 (29 m versus 11 m,
respectively), but their rates of spreading were very similar over the 2-min
duration of the analysis.
The average rate of spreading during the first 2 min of plumes DB-1 and
DB-3 was 43 cm/s. This period of rapid plume spreading and intense mixing is
attributed to wake dispersion, where the initial mixing is driven by (1)
turbulent dispersion within the wake of the barge (proportional to the speed of
the barge), (2) the velocity at which the sludge is being dumped or pumped
from the barge, and (3) density differences between the sludge and the
4-20
-------
en
Q
£
LJ
75
50--
25--
0
25
DB-3
50 75 100 125 150
TIME (seconds)
to
l_
-------
receiving water. Csanady (1981) and other investigators have estimated plume
spreading rates during this period of initial mixing, but the observations
presented here represent direct measurements from which accurate mixing
calculations can be based.
The lower panel of Figure 4-9 presents additional measurements of plume
width over a 1-h period following each event. These results were derived from
repeated aerial photographs of the plume at the location of the dye patch.
This ensured that variations in plume width were associated with the rate of
p'lume spreading, rather than variations in width at different positions along
the plume. On this and subsequent figures, T=0 h represents the time at which
the survey vessel initially stopped behind the barge to deploy the drogues and
dye, and begin profiling measurements. This T=0 h for surveys DB-1 through DB-
3 was generally 2 to 3 min after that specific portion of sludge had been
discharged from the barge.
The lower panel of Figure 4-9 illustrates that the three plumes had
roughly the same widths, and their rates of spreading were remarkably similar.
Plume DB-2 was the widest of the three plumes; plume DB-3 was initially the
narrowest but its width was equivalent to that of DB-1 within 1 h of dumping.
The fact that plume DB-3 was the narrowest of the three plumes is consistent
with the computed volume of sludge discharged per unit of plume length (lower
row in Table 4-2): 0.20 m3/m for plume DB-3 compared to roughly 0.4 m3/m for
plumes DB-1 and DB-2.
Horizontal profiling of turbidity proved to be an accurate method for
determining plume width because the natural turbidity of the near-surface
receiving water was low and remarkably constant within the dumpsite.
Measurements of plume width were obtained by (1) identifying the beginning and
end of the turbid plume water from the horizontal profile data, (2)
calculating the distance along the vessel track, and (3) making a cosine
correction for the angle between the vessel track and the orientation of the
plume axis.
Plume width estimates from horizontal profiling within plume DB-4 are
presented in Figure 4-10. The upper panel of Figure 4-10 illustrates that,
during the first hour after dumping, plume widths at 5 m increased quite
sharply to values of roughly 350 m. Measurements during the next 1/2 h
revealed that plume widths at 5 m stopped increasing, and widths began to vary
4-22
-------
to
l_
cu
I
I
Q
LJ
400-
300-
200 T
LT: iooT
o
0
DB-4 Towed Data
5m
10m A A
15m
50
\
100 150
TIME (minutes)
200
250
500
0)
400-
004-
200 +
LJ
S
ID
_J
Q_
Towed Data 5m
DB-2 A A
DB-4
0
20
40 60 80
TIME (minutes)
100
120
FIGURE 4-10.
ANALYSIS OF PLUME WIDTH FOR PLUMES DB-2 AND DB-4: RESULTS OF
TOWED DATA FOR DB-4 (UPPER); COMPARISON OF TOWED DATA FROM
PLUMES DB-2 AND DB-4 (LOWER).
4-23
-------
significantly from tow to tow. Subsequent tows (between 1.5 and 2.0 h) at
greater depths indicated that plume widths at 10 m were roughly equivalent to
those at 5 m, and plume width at 15 m was less than at shallower depths. As
time progressed, plume widths became equal at all three levels (~220 m), but
this width was significantly less than the maximum observed width of the piume
(at T*l h). Beyond 3 h, parcels of the plume could be tracked, but meaningful
measurements of plume width could no longer be obtained.
Because sludge concentrations certainly had not increased within the
plume, the reduction in plume width (and volume) indicates that sludge had
escaped from the specific volume (plume transect) that was being surveyed.
The vertical current shear, imposed by the strong currents within the seasonal
pycnocline, was apparently the mechanism for this dispersion.
The lower panel of Figure 4-10 presents a comparison of plume widths for
plume surveys DB-2 and DB-4, as derived from horizontal profile results from a
depth of 5 m. This figure illustrates that plume DB-4 was roughly 50. percent
wider than plume DB-2 which was the broadest of plumes DB-1 through DB-3.
Within 1 h, minutes after discharge, plume DB-4 had reached widths in excess of
300 m.
The results of the various aerial and horizontal profiling analyses of
plume width are summarized below.
The rates of lateral spreading were generally similar for the
four plumes studied, although their initial widths differed by a
factor of five or more.
Analyses of plume width revealed four stages of lateral
spreading:
1) From 0 to ~5 min, turbulent mixing due to wake momentum
resulted in rapid spreading with rates of approximately
40 cm/s. Turbidity within the plume was high, yet boluses of
clear receiving water were observed within the plume.
2) From 5 to ~30 min, gradual mixing due to buoyancy and oceanic
mixing processes resulted in spreading rates of ~5 cm/s.
Turbidity was relatively homogeneous across the axis of the
plume.
3) From ~30 min to 2-4 h, lateral spreading of the surface plume
was slow (~1 cm/s), but the base of the plume was elongated
due to vertical shear in the seasonal pycnocline. Thus, the
cross-sectional area of the plume increased rapidly although
4-24
-------
the width of the surface plume remained nearly constant.
Turbidity values decrease greatly during this phase.
4) A few hours after dumping (actual time dependent upon mixing
conditions), the quasi-linear plume broke into parcels of
various sizes and concentrations.
The effective lateral spreading rate during the first hour
following a dump was approximately 5 cm/s; beyond 1 h, spreading
rates were less than 1 cm/s.
Both the width and turbidity concentration within plume DB-4 were
much greater than the characteristics of the other three plumes
surveyed, which suggests that the dumping rate for plume DB-4 was
significantly greater than that of the other plumes.
4.4.1.2 Vertical Spreading
Vertical profile measurements were effective for determining the depth to
which sludge plumes penetrated during the summer survey. Results from plumes
DB-1 and DB-3 were used for analyses of the physical processes that govern the
vertical spreading of sludge plumes.
Figure 4-11 presents a composite of six vertical profiles of turbidity
(beam attenuation) obtained for plume DB-3. These profiles represent a time
series of vertical profiles that extends from the beginning of the survey
(T=0 h) to the last profile within the plume (T=8.5 h). At T=0 h within the
axis of the plume, high turbidity values (>5 m-1) extended downward from the
sea surface to a depth of approximately 9 m, below which turbidity dropped
sharply, reaching background values at a depth of about 13 m. At 0.2 h after
dumping, mixed-layer turbidity values had decreased slightly (to <5 m-1) but
relatively high values were seen to penetrate to depths of about 14 m. After
0.9 h, the plume had penetrated to 16 m and mixed-layer turbidity values
continued to decrease.
These results indicate that, within the first hour, plume DB-3 penetrated
to a depth of roughly 15 m, which corresponded with the top of the seasonal
py.nocline. Turbidity concentrations were relatively constant throughout the
mixed layer, even though concentrations were observed to decrease significantly
during the first hour.
4-25
-------
10'
L
i
30-
40
KAM ATTENUATION (!/)
a 4
t = 0.0 h
to
5
30-
40
KAM ATTENUATION II/.J
' 4
t » 02 h
10-
§
30-
ATTENUATION (t/«»
a 4
t = 0.9 h
10-
x
i
30-
40-
BCAM ATTENUATION tl/«|
a 4
t = 1.8 h
10
t
I**
£
i
30-
BCAM ATTEHUTIOM (!/!
2 4
t = 3.1 h
30-
40
KAM ATTENUATION ll/al
2 4
t = 8.5 h
FIGURE 4-11.
COMPOSITE OF VERTICAL TURBIDITY (BEAM ATTENUATION) PROFILES
HADE WITHIN PLUME DB-3; TIMES AFTER DUMPING FROM THE BARGE ARE
INDICATED.
4-26
-------
Beyond 1 h, a number of vertical profiles of plume DB-3 revealed that an
appreciable quantity of sludge was being transported laterally away from the
main, surface portion of the sludge plume. Vertical turbidity profiles within
this displaced portion of the plume revealed large subsurface maxima in
turbidity (1.8 h in Figure 4-11). The profile taken at T-1.8 h illustrates a
concentrated layer of sludge centered near a depth of 11 m, with maximum sludge
penetration to 18 m; surface turbidity values above this layer of sludge were
only slightly above background.
An additional six vertical profiles were obtained during the remaining 7 h
of event DB-3. Some of these profiles were made within the surface expression
of the plume, but after a few hours, the surface expression of the plume was no
longer evident, and horizontal profiling was used to locate concentrated
portions of sludge water, in which vertical profiles were made. The lower-
right panel of Figure 4-11 presents a turbidity profile that was made 8.5 h
after sludge dumping from the barge. This profile reveals a subsurface
turbidity maximum near 12 m, above which lies a mixed layer of very dilute
plume water.
Vertical profile results from survey DB-1 were similar to those presented
for survey DB-3. A.limited number of tows at a depth of 15 m in sludge plumes
DB-2 and DB-4 suggest that these plumes had similar vertical characteristics to
DB-1 and DB-3.
In summary, the vertical profile results from the individual plume events
indicate that
* The vertical distribution of suspended solids (as turbidity) in
the four plumes surveyed were very similar.
* Initial mixing (within 5 min after Dumping) resulted in sludge
penetration to roughly 10 m.
Vertical mixing over the first 2 h resulted in sludge penetration
to roughly 18 m, which corresponded with the top of the seasonal
pycnocline.
* After 8 h for plume DB-3, the highest concentrations of sludge
were located at a depth of 12 m, which suggests that dilution
processes above (due to winds and waves) and below-this level (due
to the strong current shear within the "jet") were stronger than
at the 12 m depth.
4-27
-------
* There was no indication that sludge settled to depths greater than
20 m, with penetration beneath the seasonal pycnocline.
4.4.2 Sludge Dilution and Transport
Calculations of sludge dilution are necessary to determine that LPCs are
being met at the site 4 h after sludge disposal, and to estimate concentration
of WQC contaminants when those contaminants cannot be measured directly in
sludge plumes. Plume volume, transmissometry, TSS, and chemical tracer data
were used in the calculation of sludge dilution for plumes monitored during the
survey. Dilution calculations presented in subsections 4.4.2.1 (plume volume)
and 4.4.2.2 (transmissometry analysis) provide estimates of dilution for the
entire plume. In contrast, dilution estimates based upon analyses of TSS data
(subsection 4.4.2.3) and chemical tracer data (subsection 4.4.2.4) from
discrete water parcels yield significantly lower dilutions, as shown below.
4.4.2.1 Dilution Based On Plume Volume
The ratio of plume volume to the volume of sludge dumped into the plume
provides the most basic method for calculating the dilution of sludge. The
volume of the plume per meter of track length was calculated from the observed
width and thickness of the plume, multiplied by a 1-m length. The volume of
sludge dumped per meter of plume length was estimated from the total volume of
sludge dumped, and the overall length of the plume (Table 4-2). This rate may
vary greatly along a single plume, but for the purpose of this analysis, the
average dumping rate is treated as a constant, average value.
This simple volume dilution analysis has inherent limitations because it
does not require conservation of mass, but it does reveal a number of basic
results which are summarized below:
Dilution 3 min after discharge from the barge was
approximately 2500:1 for all plumes. Dilutions ranged from
6,000:1 to 12,000:1 0.5 h after discharge.
Dilution progressed at a constant rate for roughly 1.0 h, but.
rates of dilution varied by a factor of 3 for the plumes
surveyed.
4-28
-------
* For plumes DB-1, 2, and 3, the dilution (plume volume) and the
rate of change of dilution (increase in plume volume) both
varied inversely with the effective dumping rate; dilutions
were highest when less sludge was dumped along a unit track
length.
* Because plume DB-4 had the largest plume volume and highest
turbidity concentrations, we can deduce that the dumping rate at
the beginning of the plume (the location of the survey event)
was significantly greater than the average dumping rate (0.28
m3/m) over the entire plume length.
Dilution estimates based upon plume volume calculations were
not useful >1.0 h after discharge because the current jet
within the seasonal pycnocline appeared to advect sludge
constituents away from the bottom of the plume.
4.4.2.2 Dilution Based On Transmissometry Data
Turbidity (transmissometry) data were also used to calculate dilution.
Horizontal transmissometry profile data from DB-4 were calibrated to
corresponding TSS data and were used to estimate a time-series of mass loading
in the plume throughout the monitoring event. Mass loading information was
then compared to initial mass loading calculated from barge discharge records
and average sludge particulate concentrations (Santoro and Fikslin, 1987) to
derive sludge dilution.
The relationship between TSS and transmissometry data was calculated for
each dumping event to verify that light transmission monitoring techniques
accurately reflected particle concentrations in sludge plumes. To develop the
relationship, individual TSS sample concentrations from each of the plumes were
plotted against the beam attenuation obtained for that sample. Figure 4-12
shows the relationship between these two parameters for each plume. Although
there is much scatter in the data, the slopes for each relationship are
similar. AH plumes display a relationship that is consistent with the
expected response of the transmissometer to suspended matter. Within the
statistical limits of this relationship, it appears that the sludge from these
four disposal events gives similar beam attenuation, suggesting that the
transmissometer output can be used to directly estimate sludge concentrations
with sewage sludge plumes. However, most of the data reflect sampling of low
turbidity water, and hence, statistically derived slopes of the relationship
4-29
-------
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CO
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527
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oc.
4-30
V'5uj 'SSi
-------
between total suspended solids and turbidity may have considerable error. A
best estimate of the relationship of TSS to beam attenuation is used to
calculate mass balance based on transmissometry data.
Figure 4-13 presents a time series of the average particulate
concentration and the particulate mass loading within a complete transect of
plume DB-4, based on transmissometry data. This figure illustrates that total
suspended solids are being lost during the time between the repeated crossings
of the plume. The rate of sludge loss from the plume appears to start
gradually, but after about 1 h, the loss is quite rapid.
Roughly 20 min after discharge, the total mass of suspended solids with a
1-m wide transect of the plume was approximately 42 kg (estimated TSS
concentration of 15 mg/L and a plume cross-sectional area of roughly 2800 m2).
This load was reduced to 7 kg about 1.5 h later, which corresponds with an 83
percent loss of solids over this time period.
The explanation for this rapid loss of sludge is that the strong currents
within the seasonal pycnocline were an effective mechanism for lateral
transport of sludge away from the axis of the plume. During plume event DB-4,
currents above 10 m were relatively weak (<15 cm/s), but between 10 and 15 m,
currents were in excess of 40 cm/s within the current "jet." In addition to
this strong vertical shear in current speed, the direction of the "jet" (~125°)
was significantly different from the direction of the near-surface flow (~60°).
The combined effect of this speed and directional shear apparently had a major
effect upon the transport of sludge within plume DB-4. The results indicate
that the bottom of the plume was rapidly and continually being advected away
from the main body of the plume, but this layer was so thin (<5 m) that it was
not evident during the horizontal profiling operations.
To determine the effect that this current "jet" had on the lateral
dispersion and dilution of the plume, the calculated TSS load information can
be used to obtain an independent calculation of plume dilution versus time.
Using the particulate load (41,760 g) calculated for the transect of plume (DB-
4) at 20 min after dumping, we obtain the following results.
* If the effective dumping rate at the position of the plume
transect was equal to the average rate over the entire plume (0.28
m3/min, see Table 4-2), then the initial TSS concentration of the
sludge within the barge would have been (~149,000 mg/L). Because
4-31
-------
cn
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CO
20
15--
10--
0
50
en
.x
Q
<
O
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GO
40--
30 J-
20 r
10-
DB-4
Towed Data
DB-4
Towed Data
0 20 40 60 80 100 120 140 160
TIME (minutes)
20 ' 40 60 80 100 120 140 160
TiME (minutes)
-ISURE 4-13.
TSS CONCENTRATION AND TSS LOAD CALCULATED FROM TRANSMISSOMETRY
WITHIN A 1-ra HIDE TRANSECT OF THE PLUME.
4-32
-------
this TSS concentration is excessively high, we suspect that the
instantaneous dumping rate was much higher than the average value.
If the initial TSS concentration of the sludge from plume DB-4
(from the New York 26th Ward facility) was ~25,000 mg/L as
reported by Santoro and Fikslin (1987), the particulate load
estimate can be used to calculate an effective dumping rate of
1.67 m3/m. This rate is roughly 6 times the average dumping rate
(0 28 m3/m) for the entire plume length. Using an average TSS
concentration of 15 mg/L within the plume at 20 min, the average
plume dilution would be ~2,000:1, a low value for the entire
plume. ,
In the absence of direct measurements of (1) the TSS concentration
within the barge and (2) the actual dumping rate from the barge
accurate plume-averaged dilution rates cannot be determined. The
results do, however, suggest that (1) the effective dumping rate
of plume DB-4 was roughly twice the average rate for the plume,
and (2) the initial TSS concentration of the sludge may have been
on the order of 90,000 mg/L, or 2 to 3 times the published
estimates.
Given the large uncertainties in the above method, rough estimates
of the plume-averaged dilution for plume DB-4 are:
~6,000:1 20 min after dumping
~15,000:1 1 h after dumping
~80,000:1 2 h after dumping
~100,000:1 3 h after dumping
4.4.2.3 Dilution Based on TSS Data
Dilution was also estimated by dividing typical sludge TSS concentrations
(Santoro and Fikslin, 1987) by the measured increase in TSS concentration over
background levels. Although actual TSS data from sludge in the barges would be
more appropriate for the calculation, the difficulty in obtaining these samples
for the survey precluded this approach. However, the use of published data
does provide mixing estimates to compare with estimates determined by other
methods.
TSS concentrations in sludge plumes at T=0 h ranged from 17 to 32 mg/L,
corresponding to initial sludge dilutions ranging from 1,030:1 to 810:1
(Table 4-3). Thus, dilutions based on TSS data from discrete samples are lower
than dilutions based upon the entire plume. Flocculation of organic matter and
nietal species, occurring when freshwater mixes with saltwater (Stumm and
4-33
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TABLE 4-3. TOTAL SUSPENDED SOLIDS IN SLUDGE PLUMES AND ESTIMATES
OF INITIAL DILUTION AT THE 106-MILE SITE
Total Suspended Solids,
Concentration (mq/L)
Plume Sludge*
Plume Maximum
at T-0 h
Background^
Increase
Over Dilution
Backgroundc at T=0
DB-1
DB-2
DB-3
DB-4
18,100
18,100
26,400
24,200
17.4
19.2
32.6
24.8
0.18
0.23
0.18
0.34
96
83
180
73
1,050:1
1,010:1
810:1
1,030:1
from Santoro and Fikslin, 1987.
t»Mean of DB-1, DB-3, and DB-4 6.0 m background TSS results.
CTSS concentration for plume divided by background concentration.
DB-1 = Sludge from Wards Island sewage treatment plant, New York City, NY.
DB-2 - Sludge from Wards Island sewage treatment plant, New York City, NY.
DB-3 3 Sludge from Port Richmond sewage treatment plant, New York City, NY.
DB-4 - Sludge from 26th Ward sewage treatment plant, New York City, NY.
4-34
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Morgan, 1981) and a process similar to that occurring naturally in estuaries.
may increase the apparent particulate concentrations relative to actual
dilution. If the process is occurring, initial mixing calculations based on
TSS may underestimate the extent of initial mixing. However, variations in
sludge dumping rates or discrepancies between actual sludge TSS content and
that reported in Santoro and Fikslin (1987) may also account for the difference
in mixing calculated by TSS concentrations.
The change in TSS concentration in the plume following dumping is
presented in Figure 4-14 for plumes DB-1 and DB-3. The TSS data suggest that
after 0.5 h, the decrease in TSS with time was linear for plume DB-1. Based on
the rate of decrease (linear regression fit; r= 0.9, n= 14), plume DB-1 would
reach ambient TSS concentrations in approximately 3 h. However, at the end of
both monitoring events, measured TSS levels remained elevated over ambient
levels. TSS concentrations determined at the end of each dumping event were
used to calculate final dilution of the sludge (Table 4-4). Dilution
estimated ranged from 11,000:1 to 25,000:1.
The TSS data displayed high variability among sample replicates collected
as the ship drifted through sludge plumes. Because of the consistency of light
transmission data over the same time period, the TSS variability probably
reflects the difficulty in collecting discrete samples in and at the edge of a
sludge plume rather than TSS heterogeneity in a given parcel of the plume.
The data demonstrate the difficulty in obtaining adequate replication using
conventional sampling techniques. Because of the variable nature of TSS data,
the above calculations were based on individual samples rather than average
values of several replicates. ,
4.4.2.4 Dilution Based on Chemical Tracer Data
Chemical signatures of sludge to trace the sludge as it was dispersed at
the site were also used to measure dilution. Copper, iron, lead, and zinc were
selected as chemical tracers based on their relatively high concentrations in
sludge dumped at the site (O'Connor et al., 1985) and their ease of analysis.
Chemical tracer data are used to support and confirm nearfield fate analyses
based on other measurement techniques. Additional analyses were, performed on
4-35
-------
20
15-
en
tn
in
O
10-
5-
8
§
0
0.0
0-5 1.0 1.5 2.0 2.5 3.0
TIME, h
3.5
FIGURE 4-14A. TOTAL SUSPENDED SOLIDS CONCENTRATIONS MONITORED DURING DUMPING
^NJnS?'U?LUDGE FROM WARDS ISUND SEWAGE TREATMENT PLANT
ntH TuKK.. Nil. *
35
30 -*
jt
25-
o
DB3
o
10- 3
5- °
§
0.0'
1 .0
2.0 3.0
TIME, h
4.0
IGURE 4-14B. TOTAL SUSPENDED SOLIDS CONCENTRATIONS MONITORED DURING DUMPING
EVENT DB-3 (SLUDGE FROM PORT RICHMOND SEWAGE TREATMENT PLAN,
NhH YORK, NYJ.
4-36
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TABLE 4-4. TOTAL SUSPENDED SOLIDS IN SLUDGE PLUMES AT THE
106-MILE SITE MONITORED AFTER DUMPING
Plume
DB-1
DB-2
DB-3
DB-3
DB-4
DB-4
Time
After
Dilution
(h)
2.88
4.3
4.18
4.35
4.72
4.72
TSS
Depth Concentration
(m) (mg/L)
6
6
6
10.4
6
10.4
1.06
0.95
2.5
1.9
3.5
1.6
Increase
Over
Background*
4.9
3.1
12.9
9.2
10.3
3.6
Dilution
of Sludge^
2.1x104
2.5x104
1.1x104
1.5x104
2.4x104
1.9x104
aCalculated by dividing final sludge plume TSS concentrations by ambient
TSS values.
bCalculated by dividing source levels (Santoro and Fikslin, 1987) by final
sludge plume TSS concentrations.
4-37
-------
chemical tracers to determine which, if any, element is more suitable for
tracing the sludge.
Dilutions at T=0 h for two dumping events were calculated by comparing
concentrations of chemical tracers in sludge plumes with average concentrations
of those tracers in the sludges being dumped (Santoro and Fikslin, 1987). As
with similar calculations based on TSS data, actual tracer data from sludge in
the barges dumping at the site would be more appropriate for mixing
calculations, but the difficulty in obtaining sludge samples for the summer
survey precluded this approach. However, the use of published data does
provide mixing estimates to compare with estimates determined by other methods.
As with TSS, the variability in chemical tracer data made it difficult to
calculate mass balances. Dilution calculations are presented below.
Concentrations of the metal tracers, copper, lead, and zinc, in sludge
plumes DB-2 and DB-3, and estimates of dilution are presented in Table 4-5.
The calculated initial dilution varied both between plumes and for each tracer
within a plume. Initial dilutions calculated for DB-2 ranged between 2,600:1
and 6,300:1. Initial dilution calculated for DB-3 was lower, ranging between
400:1 and 1,100:1 dilution depending on the element used in the calculation.
Dilutions calculated from samples collected at T=4.3 h range from 25,000:1 to
52,000:1 for plume DB-2, and from 1,900:1 to 6,300:1 for plume DB-3.
Metal concentrations in the receiving water within the sludge plumes DB-2
and DB-3 increased between 90:1 and 2,340:1 above background at T=0 h. The
amount of increase varied with the sludge being monitored and with each metal
for a given sludge. No one tracer gave consistently high relative increases
between the two events being monitored, reflecting the variability in metal
concentrations of the source material. However, of the three metals analyzed
at TsO h, copper showed the lowest relative increase over ambient
concentrations for both dumping events.
Metal concentrations within the plumes monitored behaved similarly after
initial dilution and decreased exponentially with time as illustrated in Figure
4-15. The mean exponential decay rate derived from the rate of decay for each
element for plume DB-3 was relatively constant (0.51 * 0.02 h-1). Thus, under
the conditions found at the 106-Mile Site during this one event, the
concentration of tracers in the sludge plume decreased by a factor of 2
(halved) every hour following disposal.
4-38
-------
TABLE 4-5. ESTIMATES OF DILUTION AT T=0 h AND T=4.3 h BASED ON
METAL TRACER CONCENTRATIONS
T=0 h
Source'
Event Concentrations3
DB-2
DB-3
DB-2
DB-3
DB-2
DB-3'
52,
50,
20,
19,
35,
48,
700
900
700
300
100
400
T=4.3 h
Initial Initial
Sludge Sludge Sludge Sludge
Plume Dilution Plume Dilution
Concentrations Concentrations
14
50
3
51
13
48
.7
.0
.3
.5
.4
.4
3,600:
1,000:
6,300:
400:
2,600:
1,000:
Copper.
1
1
Lead. \
1
1
Zinc. \
1
1
£Q/L
2
11
tq/L
0
10
*q/L
1
7
.1
.2
.4
.4
.3
.7
25
4
52
1
27
6
,000:
,500:
,000:
,900:
,000:
,300:
1
1
1
1
1
1
aSantoro and Fikslin, 1987.
4-39
-------
60
50
40 A
20-
.0--
6m
010m
\
V
D.O 2.0 4.0 6.0
Time after disposal, h
60
5
a.
"5
40-\
20-
6m
o 10 m
\
\
'-+
0.0 2.0 4.0 6.0 8.0
Time after disposal, h
60
40 f
M
"5
£ 20 T
8.0 10.0
10.0
6 m
010m
\
\
0.0 2.0 4.0 6.0
Time after disposal, h
8.0
10.0
i:J?T 4-15. COPPER, LEAD, AND ZINC CONCENTRATIONS MONITORED DURING
DUMPING EVENT DB-3 (SEPTEMBER 3, 1987). DASHED (--) LINE
DEPICTS MEAN EXPONENTIAL FIT.
4-40
-------
To determine which, if any, element was significantly more useful as a
chemical tracer of sewage sludge, metal concentrations from individual samples
were plotted against one another to determine how well the results for one
metal predicted the behavior of the other tracer metals. Metals were plotted
against iron, the metal with the highest concentration in plumes DB-2 and DB-3
at T=0 h. A strong correlation between iron and the other three metals
analyzed was found for each plume event (Figure 4-16). These results show
striking consistency in metal behavior within each plume and tentatively
suggest that analysis of one metal can be used to predict the nearfield fate of
the other metals in sludge plumes over similar time frames, provided metal
ratios are established for each plume.
Figure 4-16 also' illustrates that metal ratios may be used to develop.
sludge "signatures" that can be used to trace and identify individual sludge
plumes throughout the nearfield, short-term monitoring, the characteristic
ratios have significant potential for identification of individual sludge
plumes when multiple barges are dumping at the site. The signature concept
also has potential for long-term fate studies (i.e., monitoring the change in
sediment trap metal ratios against oceanic "control" values) and potential for
monitoring the operation of individual treatment plants in relation to the
effectiveness of point-source control measures.
4.4.2.5 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 of the site. In addition to the use of current
profile data for prediction of rates of sludge plume advection, continual
contact with the plumes during the four sampling events (DB-1 through DB-4)
yields a direct measurement of the time that each of the plumes crossed the
site boundaries. Figure 4-17 illustrates the movement of sludge plumes DB-1
and DB-2 during the individual plume-tracking events; Figure 4-18 illustrates
the movement of plumes DB-3 and DB-4. The information shown for each plume
includes (1) the positions of initial (T=0 h) and final contact with the plume,
(2) elapsed time (in hours) since dumping from the barge, and (3) the initial
orientation of the plume at the initial position of the tracking event.
4-41
-------
5
o 20
100 150 200
Total Fe, pq/L
250
300
4
50
100 150
Total Fe.
200
250
300
FIGURE 4-16.
i - ,. <... i ^ O
50 100 150 200
Total Fe, pq/L
250
300
DIAGNOSTIC TRACER RATIOS FOR SLUDGE PLUMES DB-2 (SLUDGE
FROM WARDS ISLAND SEWAGE TREATMENT PLANT, NEW YORK CITY,
NY) AND DB-3 (SLUDGE FROM PORT RICHMOND SEWAGE TREATMENT
PLANT, NEW YORK CITY, NY).
4-42
-------
33"
39* O'N
38'55'N
DB-1
t-4.0
t-0
. INITIAL
^ PLUME
HEADING
"I
i
i
72 5' W
106-Mile Site
72 O1 H
71 55' W
39' 2'N
39 O'N
3B 55'N
DB-2
t-0
INITIAL
PLUME
HEADING
t - 4.1
106-Mile Site
72 5' W
72 0' X
71 55' X
FIGURE 4-17.
SUMMARY OF PLUME AOVECTION FOR PLUMES DB-1 AND DB-2. HOURLY
POSITIONS OF THE PLUME ARE INDICATED, AS WELL AS THE INITIAL
HEADING OF THE PLUME.
4-43
-------
39 2'N
39 O'N
38 55'N
DB-3
106-Mllt Site
INITIAL I
PLUME
HEADING
72 5' W
72' 0' W
t-8.6
71 55' W
39 2'N
39 O'N
38 55'N
INITIAL
PLUME
HEADING
-1 1 1
r- 1 r
DB-4
t-3.3
72 5'
106-Mile Site
72 0'
71*55' W
FIGURE 4-18. SUfHARY-OF PLUME ADVECTION FOR PLUMES DB-3 AND DB-4. HOURLY
, POSITIONS OF THE PLUME ARE INDICATED, AS WELL AS THE INITIAL
HEADING OF THE PLUME.
4-44
-------
The results of plume advection can be summarized as follows:
Plume DB-1 remained within the site for at least 4 h after it was
dumped at the northern boundary of the site.
The remaining three plumes crossed the eastern boundary of the
site within 2 to 3 h after they were dumped near the center of the
site (near 72°02'W).
Plume advection toward the east was in direct opposition to the
expected mean (westward) flow direction of slope water at the
site. Eastward advection was probably related to the anticyclonic
flow around the warm-core eddy situated to the east (or southeast)
of the site.
* Had real-time current data been used to direct dumping operations
toward the western boundary of the site, all plumes would have
remained within the site boundaries for at least 4 hours after
dumping.
The current regime that was encountered during the survey may have been
atypical for the 106-Mile Site, but during these events, strong near-surface
currents can move sludge plumes out 6f the site in a few hours. The observed
currents may have represented a worst-case for plume advection because the
currents were directed across the narrow, east-west dimension of the 106-Mile
Site. However, during the passage of a warm-core Gulf Stream eddy, near-
surface currents can reach speeds 3 to 4 times greater than those observed
during the survey, and plume residence times within the site may be reduced to
an hour or less.
4.5 HATER QUALITY MEASUREMENTS
A primary concern of the 106-Mile Site monitoring program is 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 or pH at the site. The survey
addressed water quality issues through the analysis of water samples collected
in sludge plumes for WQC contaminants. Although samples for the analysis of
contaminants for which there are EPA water quality criteria were collected in
4-45
-------
all four sludge plumes monitored, only two sets of samples, those from DB-2 and
DB-3, were analyzed. Additional monitoring was conducted to verify that the
disposal of sludge does not cause a significant depletion of dissolved oxygen
content of the water and to monitor the levels of the microbiological tracer,
C. perfringens; pH was not monitored. A summary of water quality findings is
presented below. A complete set of water quality data is presented in
Appendix D.
4.5.1 Comparison to Water Quality Criteria
Results of the analysis of samples collected within plumes DB-2 and DB-3
indicate that all organic contaminants and all but two metal contaminants
(copper and lead) were below water quality criteria approximately 4 h after
disposal. Copper levels exceeded WQC in both plumes studied, but lead
concentrations exceeded WQC only in DB-2. Mercury concentrations in both
sludge plumes were within a factor of 2 of WQC at 4 h, whereas nickel
concentrations were within a factor of 2 of WQC after 4 h in plume DB-3 (Table
4-6). Concentrations of other metal WQC contaminants and all organic WQC
contaminants were well below WQC levels in both sludge plumes.
Sludge plume DB-3 was advected outside the site within 4 h, and although
water samples were not collected at the site boundary, concentrations of
contaminants in the plume could be calculated based on chemical tracer. Using
the mean tracer dilution rate for sludge plume DB-3 (Section 4.4.4) and
reported contaminant concentrations in sewage sludge (from the Port Richmond
sewage treatment plant), (Santoro and Fikslin, 1987), copper met marine WQC 5.2-
h after disposal, whereas lead, mercury, and nickel met WQC 4.1 h, 3.25 h, and
0.9 h after disposal, respectively. Because sludge plume DB-3 was advected
outside of site boundaries at 2.5 h, calculated concentrations of copper, lead,
and mercury exceeded WQC outside the site. Other metal and organic
contaminants were calculated to be below marine WQC when the plume was
transported beyond site boundaries.
Because Santoro and Fikslin (1987) presents contaminant information for
all 19 sewage treatment plants using the 106-Mile Site, the data can be used
to predict contaminant levels in site waters assuming sludges from other
plants were Humped under the same conditions, resulting in the same initial and
4-46
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4-47
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continuing dispersion as determined for event DB-3. The average concentration
of eight metals in sludge from each treatment plant was used to determine the
T=0 h concentration (assuming initial dilution of 1000), and the mean
exponential rate of tracer decay in the plume (0.51 x 0.02 h-1, Section
4.4.2.4) was used to calculate the expected concentration of each metal in the
plume 4 h after disposal. These estimates were compared to EPA WQC. For the
19 sewage treatment plants reported in Santoro and Fikslin (1987), 18 would not
meet the marine water quality criteria for copper under the conditions
prevailing during dumping event DB-3. The results of this exercise are
presented in Table 4-7.
Because the calculated rate of tracer decay with time in plume DB-3 is
based on few data points, and because the published data may not reflect
changes in contaminant levels in current sludges, the results in Table 4-7 must
be considered an estimate. TSS data show a more rapid rate of dispersion
during dumping event DB-3, and using TSS dispersion rates, fewer sludges would
exceed HQC. Because different oceanographic conditions may be more or less
dispersive, caution must be used in drawing conclusions from dispersion rates
calculated from dumping event DB-3. However, Table 4-7 does illustrate that
of the contaminants for which there are marine water quality criteria, only
arsenic and cadmium are not of concern vis-a-vis the 106-Mile Site monitoring
program. Calculations show that other elements, to varying degrees, exceed or
approach marine WQC 4 h after disposal of one.or more typical sludges at the
106-Mile Site.
4.5.2 Dissolved Oxygen
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. Analyses of oxygen
data from within the various plumes revealed extremely small reductions
(0.3 ml/L) of oxygen during the first hour after sludge discharge, but the
magnitude of these variations was well below the expected accuracy of the
sensor (±0-1 ml/I). These oxygen reductions could only be attributed to the
sludge plumes when the data were analyzed along horizontal transects through
the plumes.
4-48
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TABLE 4-7 NUMBER OF SLUDGE PLUMES NOT MEETING EPA WATER
QUALITY CRITERIA 4 h AFTER SLUDGE DISPOSAL AT THE
106-MILE SITE. NON-COMPLIANCE BASED ON MEAN
CONTAMINANT CONCENTRATIONS IN SLUDGES FROM 19 SEWAGE
TREATMENT PLANTS IN THE NEW YORK METROPOLITAN AREA
Santoro and Fikslin, 1987), AND MEAN DISPERSION
RATES (FROM METAL TRACER DATA, SLUDGE PLUME DB-3)
Element
Number of Sludoe Plumes
Above WQC
Within 3x WQC
Arsenic
Cadmium
Chromium
Copper
Mercury
Nickel
Lead
Zinc
0
0
0
18
5
0
4
0
0
0
2
19
13
1
8
1
4-49
-------
Figure 4-19 presents a stackplot of horizontal profile measurements versus
distance along a transect through plume DB-4. The top of this figure
illustrates the high turbidity (beam attenuation) within the plume. Visual
inspection of the salinity, sigma-t, and oxygen profile results reveals reduced
values for each parameter at the same location as the high turbidity values.
These results demonstrate that sludge plumes are less saline and have lower
oxygen values than receiving water. The observed temperature variability is
presumed to be associated with natural variability, as the sludge apparently
had temperatures equivalent to the receiving water. Thus, salinity is the
controlling factor in plume density, and therefore, the plumes were less dense
than the receiving waters near the sea surface. This information also supports
the observation that sludge plumes did not sink beyond the seasonal pycnocline.
4.5.3 Clostridium perfringens
, ''i
A microbiological tracer of sewage sludge, C. perfringens, was found at
elevated levels in sludge plumes throughout each plume tracking event
(Table 4-8). For one sludge plume (DB-1), C. perfrinqens levels throughout the
survey remained too numerous to count, indicating that C. perfrinqens may be
the most sensitive sludge tracer used on the survey. The data also indicate
that C. perfrinqens concentrations in sludges may vary dramatically, suggesting
that levels of pathogens in sludges may also vary. C. perfrinqens is a spore-
forming anaerobe thought to be associated with forms of food poisoning (Higgins
and Burns, 1975). Because it exists as a cyst, this species is thought to be
more viable than other bacteria and is useful as a sewage tracer (Cabelli and
Pederson, 1982). C. perfrinqens levels in sludge plumes at the site may not
reflect levels of other more harmful pathogens. C. perfrinqens was not found
in any out-of-site control samples analyzed. Complete C. perfrinqens data are
presented in Tables C-5 through C-8 in Appendix D.
4-50
-------
LENGTH OF TRANSECT (meters)
100
ISO
200
o
I
2 -
1 -
0
21.70
21 .ta
21.M
21.55
21 JO
315
SS.4
O
2X0
4.U
4.50
FIGURE 4-19.
VARIATIONS IN WATER PROPERTIES ALONG A TRANSECT OF PLUME DB-4
THAT WAS MADE 55 MINUTES AFTER DISCHARGE FROM THE BARGE.
REDUCTIONS IN SALINITY, SIGMA-T, AND OXYGEN CORRESPOND WITH
HIGH TURBIDITIES (BEAM ATTENUATION) WITHIN THE PLUME.
4-51
-------
TABLE 4-8. CONCENTRATIONS OF C perfrinoens IN THE SLUDGE PLUMES
AT T=0 AND BETWEEN 4 AND 7 h AFTER DISPOSAL (RFSIII TS
ARE BASED ON THE MAXIMUM OBSERVED IN THESE* 0F
REPLICATE SAMPLES FOR THE SAMPLE PERIOD.)
DB-1
DB-2
DB-3
DB-4
TNTCa
>20?c
257
TNTC
TNTCb
292d
150f
209
3006
TNTC - Colonies too numerous to count.
"Number of colonies estimated as >1500/100 mL
^Number of colonies estimated as >820/100 mL
' repl1cate' coloni« ^ two of the three replicates
r
dCollected at T=4.3 h.
eCollected at 10 meters, T=7.25 h.
^Collected at 6m, at T=4.18 h.
9Collected at 6m, T=4.72 h.
4-52
-------
4.6 OBSERVATIONS OF CETACEANS AND MARINE TURTLES
Five species of cetaceans, including two species of whales and three
species of dolphins, were observed in slope and shelf-edge waters. There were
no marine turtles observed during the survey. A complete discussion of results
is included in the site condition report ( EPA , 1987f).
4-53
-------
-------
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
1987a). 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
summer survey are discussed in terms of hypotheses addressing issues
associated with Tier 2 of the monitoring plan. The hypotheses H03 through H09
are divided into two categories: permit compliance and impact assessment.
Permit Compliance: Nearfield Fate
H03: Concentrations of sludge and sludge constituents outside
the site are below the permitted LPC and WQC at all times.
The summer survey demonstrated that sludge dumped in the
site can be transported outside site boundaries .before all
5-1 '
-------
constituents are diluted below LPC and WQC. This was
demonstrated for the sludge constituents copper and lead
and are predicted for mercury and nickel. Organic sludqe
constituents were significantly below WQC.
H04: Concentrations of sludge and sludge constituents within the
site are below the permitted LPC and WQC 4 h after
disposal.
Although oceanographic conditions at the site during the
summer survey were considered dispersive, concentrations of
the sludge constituents copper and lead exceeded WQC 4 h
after disposal. WQC for mercury would also be exceeded in
sludge plumes, from some sewage treatment plants using the
5 1 L 6 '
H05: Pathogen levels do not exceed ambient levels 4 h after
disposal.
The microbial tracer, C. perfrinoens. exceeded ambient
levels in all sludge plume water collected 4 h or more
after disposal. C. perfrinoens is not a pathogen, but a
conservative microbial tracer of sewage; therefore C
perfrinoens data are not conclusive proof that pathogen
levels are being exceeded 4 h after disposal. The data
suggest that a suitable replacement for C. perfrinoens be
developed for future nearfield fate surveysT -
Impact Assessment; Nearfield Fate
H06: Sludge particles do not settle in significant quantities
beneath the seasonal pycnocline (50 m) or to the 50-iu depth
at any time, within the site boundaries or in an area
adjacent to the site.
Sludge penetration below 20 m was not observed on the
S2'.?V!2 * h^fter Slu?9e dischar9e. Because of the
strong jet" in the pycnocline during the time of the
survey, sludge could have been carried away in the
pycnocline and potential settling not observed.
0
th\re9lon. vertical profiles of natural turbidity
a subsurface maximum situated within the seasonal
pycnocline. This suggests that surface-dumped particulate
matter may accumulate within the seasonal pycnocline durinq
summer and coexist with natural pi anktonic species.
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
5-2
-------
Concentrations of the sludge constituents copper and lead
exceeded WQC 4 h after disposal. WQC for mercury would
also be exceeded in sludge plumes from some sewage
treatment plants using the site. Although sludge could not
be tracked for more than 9 h after disposal, calculations
of sludge dispersion, indicate that all measured sludge
constituents would reach ambient concentrations within 1
day after disposal.
H08: 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.
The summer survey demonstrated that sludge dumped in the
site can be transported outside site boundaries before all
constituents are diluted below LPC and WQC. This was
demonstrated for the sludge constituents copper and lead
and predicted for mercury and nickel. Organic sludge
constituents were significantly below WQC. Calculations of
dispersion indicate that all measured constituents would
reach ambient concentrations within 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 observed depression in dissolved oxygen levels in
sludge plumes is minor and at the limit of instrument
resolution. The observed depression of dissolved oxygen is
that predicted by simple mixing models, and not the result
of depletion caused by chemical oxygen demand (COD) or
biological oxygen demand (BOD). During the summer survey,
pH was not monitored in sludge plumes.
5.2 EVALUATION OF MEASUREMENT TECHNIQUES
(
Because the September 1987 survey was the first field application of
proposed technical guidance for plume-tracking activities to be conducted as
part of the 106-Mile Site monitoring program, an 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 Section 2.0) are evaluated in terms
of the success of the September 1987 survey:
5-3
-------
K* 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 OSV
Andgrssa 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.
U?Uli°r-IH t!?e m?vePent and dispersion of the marked sludge
Swift *Servations froro the OSV Anderson and I
mo were successful in monitoring the
movement and dispersion of the plume. Aerial photo-
ufo^?^""06 Proved to be a usef"l tool for determining
lateral dispersion and orientation of the plume.
Acquisition of in situ transmissometry and acoustics data
data *
Transmissometry was the most sensitive and reliable real-
time tracking method and provided the most data for
nearfield fate analyses. Horizontal transmissometry
profiling (transmissometer on a V-fin depressor) allowed
continuous profiling while the ship was under power and
making reciprocal passes through the sludge plume.
Acoustics pr filing (27 and 300 kHz) of two sludge plumes
I EPA , I987f) provided good quality data. However the
data were not quantitative, and because the acoustics
profiler and the transmissometer could not be used at the
same time on the OSV Anderson, acoustic profiling was not
hSrZmt0!! the SUr-ey' If aPPP^ate transducers can be
hull -mounted, acoustic profiling may provide useful
supplemental information to transmissometry. However
aSS??r°nrn5?i?OWe? °f ^ransmi'ssometry for plume tracking,
method profl1in9 1S not recommended as a primary survey
For the September 1987 survey, seawater was pumped throuoh a
conventional UV fluorometer. Air bubbles in thS seawSe?
an3 ?hP°^!!UHlly injer^ered with fluorescence measurements
and the method was abandoned before its utility for plume
tracking was uly investigated. A flurometer would be
5-4
-------
Collection of samples for chemical and biological tracers
and total suspended solids to determine actual
concentrations of sludge components and dilution of these
components.
The chemical tracers and TSS proved to be valuable
measurements for determination of nearfield fate of disposed
sludge. Without these measurements, transmissometry data
could not be related to actual contaminant levels at the
site.
Acquistion of satellite-derived ocean frontal analyses, CTD
profiles, and measurements of current shear to determine the
oceanographic conditions that may 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 was extremely useful at sea for
predicting sludge plume behavior. CTD profiles and current
shear measurements proved necessary for interpretation o.f
plume-tracking 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 positiot of the ship in relation to the plume, real-time
navigation was an indispensible aid to the plume-tracking
survey.
5-5
-------
-------
6.0 REFERENCES
Bisson, J.W. and V.J. Cabelli. 1979. Membrane Filter Enumeration
Method of Clostridium perfrihgens. 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
oerfringens spore densities. In: Conference Proceedings of the
Marine Pollution Sessions of Oceans '82. Pp. 995-999. Marine
Technology Society and the Institute of Electrical and Electronic
Engineers Council on Ocean Engineering, Washington, DC.
Csanady, G.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, 1., B. Magnusson, 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.
EPA.
EPA.
EPA.
EPA.
1987a. Strategy for Plume Tracking Methods at the 106-Mile Site.
Environmental Protection Agency Oceans and Coastal Protection
Division (formerly OMEP), Washington, DC.
19875. Analytical Procedures in Support of the 106-Mile Deepwater
Municipal Sludge Site Monitoring Program. Environmental
Protection Agency Oceans and Coastal Protection Division (formally
OMEP), Washington, DC.
1987c. Final Report on Analysis of Baseline Seawater and Sediment
Samples from the 106-Mile Deepwater Municipal Sludge Site.
Environmental Protection Agency Oceans and Coastal Protection
Division (formally OMEP), Washington, DC.
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 (formally OMEP), Washington, DC.
1987e. Site Condition 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.
6-1
-------
EPA.
EPA.
EPA.
EPA.
1987f. Final Report on Analytical Results of Samples Collected
During the 1985 North Atlantic Incineration Site (NAIS) Survly
Environmental Protection Agency Oceans and Coastal Protection
Division (formerly OMEP), Washington, DC.
1988. Final Report of Analytical Results of the 106-Mile
Deepwater Sludge Dumpsite Survey-Summer 1986. Environmental
OMEP) Wash?nnton°CDCnS ^ C°aStal Protection Division (formally
1992a. Final Draft Monitoring Plan for the 106-Mile Deepwater
cUSJ°i!!n Slud9e site- Environmental Protection Agency. EPA 842-
o 32 009.
* Plan for the 106-Mile Deepwater
Sludge Site Monitoring Program. Environmental
Protection Agency. EPA 842-S-92-010
?n «J2Jt!; inJ^JS8""; 9?7' Picomolar mercury measurements
in seawater and other materials using stannous chloride reduction
S!afeJ?ld amal9amation with gas phase detection. Mar.
tUi2Z7 243.
n ,R'5 B-rns> 1975> The C^mistry and Microbiology of
Pollution, Academic Press, New York, NY. 148 pp.
rnfM M-Jke-s J-£- Pau1' and V-J- B1erman- 1985- A
strategy for Monitoring of Contaminant Distributions Resulting
From Proposed Sewage Sludge Disposal at the 106-Mile Ocean
Disposal Site. Mar. Env. Res. 16:127-150.
atd'J- F^slin. 1987. Chemical and lexicological
in
Aquatic chemistry'
6-2
-------
APPENDIX A
-------
-------
A.I DATA QUALITY REQUIREMENTS AND OBJECTIVES
The data requirements for chemical analysis are summarized in Table 3-2.
Accuracy of the chemical analyses were determined by analysis of procedural
blanks and certified reference materials, when available. 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 were determined by
analysis of duplicate samples.
The accuracy of Clostridium perfrinqens and total suspended solids (TSS)
results could not be determined from independent standards because certified
reference standards are not available. Analysis of spiked samples for these
parameters is not feasible.
A.2 QUALITY CONTROL RESULTS
A.2.1 Total Suspended Solids
Analysis of duplicate TSS samples showed precision of less than 10
percent relative percent difference (RPD). The precision was consistent
throughout the wide range in TSS concentrations; e.g., TSS mean = 24, RPD =
6.0; TSS mean = 0..79, RPD = 3.8. Six blank filters processed in the field
resulted in mean TSS concentrations of 0.3 * 0.9 mg/L, reflecting the
difficulty in obtaining accurate TSS determinations of low turbidity water.
The procedural blank values are thought to result from changes in humidity
affecting both tare and final filter weights. TSS results were not corrected
for blanks. The precision was within the objectives for the analysis of TSS.
However, because of tne absence of reference material, accuracy could not be
determined.
A.2.2 Metals
The method detection limits, determined during the analysis.of the
samples for trace metal concentrations are listed in Table A-l. All detection
A-l
-------
limits are sufficient to determine the concentration of the metals analyzed at
background oceanic levels. The detection limits obtained are within the
objectives listed for this project, except for arsenic and mercury. The
detection limits achieved for these two elements were, however, sufficient to
provide detectable concentrations of these elements for all samples analyzed.
Results of procedural blanks (Table A-2) indicate most metals were analyzed
without significant contaminant contribution to the sample. A consistent
contribution from the analytical procedure was found for iron, mercury, and
zinc. Sample results were corrected for these blanks. Results of duplicate
analyses indicate excellent precision (<10 percent as the RPD) was obtained in
the laboratory (Table A-3). Silver (67% as the RPD) and cadmium (24% as the
RPD) had relatively poor precision due to the extremely low concentrations
found in the samples. Chromium results were also more variable (RPD = 24).
Recovery of matrix spikes (Table A-4) was excellent, generally ranging
between 80 and 120 percent of the known addition. Lower recoveries of silver
(51%) were observed, and iron and lead recoveries were variable, with
V ' . ' ' , i
significant overrecovery observed in several samples. Metal recoveries from
certified seawater samples (Table A-5) were higher than observed for matrix
spikes. Silver is not certified in standard seawater, therefore no estimate
of accuracy is available from this quality control check.
A.2.2 ORGANIC COMPOUNDS
Method detection limits for the pesticides and polychlorinated biphenyl .
(PCB) analysis are shown in Table A-6. Detection limit objectives were met
for these compounds. Recoveries of organic compounds were determined at two
steps of the extraction procedure, during field extractions and within the
laboratory. Field recoveries were determined by the addition of a known
amount of decachlorobiphenyl to each sample. The recoveries determined for
this compound were low and variable (Table A-7), ranging between 6 and 58
percent. Sample results are not corrected for this extraction efficiency. In
tue laboratory, a suite of compounds were spiked into a sample and the recovery
efficiency determined (Table A-8). Recoveries were excellent, with the
exception of cc-endosulfan and /S-endosulfan. The results indicate that the
cleanup step (silica-alumina column chromatography) necessary to achieve the
A-2
-------
required detection limits allowed successful recovery of all analytes except
for the two with low recoveries.
A-3
-------
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T3
-------
TABLE A-l. METHOD DETECTION LIMITS FOR ANALYSIS OF SAMPLES
FOR TRACE METAL CONCENTRATIONS DURING PLUME-
TRACKING EXERCISES SEPTEMBER 1987
Analyte
Detection
Liarit 0»g/L)
Arsenic
Cadmium
Chromium
Copper
Iron
Lead
Mercury
Nickel
Selenium
Silver
Zinc
0.68
0.0009
0.009
0.006
0.06
.009
.002
0.03
0.03
0.002
0.003
0.
0.
A--
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LU
tO
to
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to
tl
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to
CL a.
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A-6
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A-7
-------
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A-8
-------
TABLE A-6. METHOD DETECTION LIMITS FOR ANALYSIS OF ORGANIC COMPOUNDS
FROM 100-L SAMPLES DURING THE PLUME-TRACKING EXERCISES.
SEPTEMBER 1987
Analyte
Cl2(8)a
C13U8)
Cl3(28)
Heptachlor
C14(52)
Aldrin
C14(44)
Cl4(66)
o,p'-DDE
Cl5(101)
Chlordane
Dieldrin
p.p'-DDE
. C14(74)
o,p'-DDD
C15(118)
p,p'-DDD
o.p'-DDT
Cl6(153)
Cl5(105)
p.p'.-DDT
Cl6(138)
C15U26)
Cl7(187)
C16U28)
Cl7(180)
Cl7(170)
Cl8(195)
Clg(206)
a-Endosulfan
Endosulfan sulfate
Detection Limit (ng/L)
0.004
0.001
0.003
0.001
0.001
0.001
0.002
0.003
0.001
0.002
0.002
0.001
0.002
0.013
0.008
0.002
0.004
0.003
0.002
0.007
0.001
0.003
0.010
0.005
0.007
0.000
0.001
0.001
0.000
Not determined
Not determined
refer to PCB level of chlorination. The number
refers to the isomer number, IUPAC nomenclature.
.A-Q
-------
TABLE A-7. RECOVERY OF DECACHLOROBIPHENYL SPIKED INTO 100-L
SAMPLES OF SEAWATER PRIOR TO EXTRACTION IN THE FIELD
Plume
or
Event
S8
S8
DB-2
DB-2
DB-2
DB-2
DB-2
DB-2
DB-2
DB-2
DB-2
DB-2
DB-2
DB-2
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
Depth
()
6.0
6.0
6.0
6.0
6.0
24.5
24.5
24.5
6.0
6.0
6.0
10.1
10.5
10.3
6.0
6.0
6.0
6.0
6.0
6.0
7.0
5-7
^I^^KKEB
Rep.
No.
1
2
1
2
3
1
2
3
1
2
3
1
2
,3
1
2
3
1
2
3
1
2
Start
Time
2051
2057
0722
0730
0738
2133
2212
2236
1456
1505
1510
1822
1833
1847
0900
0911
0918
1535
1543
1551
1613
1644
Tine
After
T-0 (h)
BKG
BKG
BKG
BKG
BKG
BKG
BKG
BKG
4.5
4.6
4.7
7.9
8.1
8.3
BKG
BKG
BKG
4.4
4.5
4.7
5.0
5.6
Not
Not
37.6
30.6
33.2
36.0
15.3
25.6
57.9
11.8
11.3
6.4
7.6
22.4
28.7
30.5
30.8
23.5
27.0
15.2
Percent
Recovery
available
available
33.73
23.3
of two replicate analyses.
BKG denotes background samples.
A-10
-------
TABLE A-8. RESULTS OF BLANK SPIKE ANALYSIS, ORGANIC COMPOUNDS
Compound
Percent
Recovery
Pesticides
PCBs
Heptachlor
Aldrin
Heptachlor epoxide
cc-Endosulfan
Dieldn'n
4,4'-DDE
Endrin
/?-Endosu1fan
4,4'-DDD .
Endrin aldehyde
Endosulfan sulfate
4,4'-DDT
Methoxychlor
Cl2(8)
Cl3(18)
Cl3(28)
C14(52)
Cl4(44)
Cl4(66)
cisdoi)
Cl5(118)
Cl6(153)
C15(105)
Cl6(138)
C17(187)
Cl6(128)
C17(170)
Cl8(195)
Clg(206)
110
111
8.6
120
114
9.6
91.8
96.4
117
96.7
105
102
92.7
144
110
162
145
105
101
102
101
96.2
89.3
A-11
-------
-------
APPENDIX B
CTD TRANSECT TO THE 106-MILE SITE
WATER MASSES DURING PLUME-TRACKING SURVEYS
-------
-------
CTD Transect to the 106-Mile Site
During the eastbound transit to the 106-Mile Site on August 31, 1987, a
series of seven CTD profiles was made along a line extending from the edge of
the continental shelf, through the northern end of the 106-Mile Site, to a
position roughly 8 miles northeast of the site (Figure B-l). The primary.
objective of this transect was to locate the position of the shelf water/
slope water front (east of the 106-Mile Site), as well as to determine
whether a warm-core Gulf Stream eddy was situated near the eastern boundary
of the site, as suspected from interpretations of satellite thermal imagery.
To illustrate variations in water properties along the eastbound CTD
transect, Figure B-2 presents vertical profiles of temperature (top panel)
and salinity (middle panel) versus depth for Stations 1, 4, and 5 along the
transect. Stations 1 and 5 are located at the edge of the continental shelf
and within the 106-Mile Site, respectively; Station 4 is shown for comparison
because it exhibited anomalous water mass properties.
The upper panel of Figure B-2 illustrates that the surface mixed layer
at the offshore stations was more than 1°C warmer than surface waters at
Station 1, and that the mixed layer deepened toward shore. Profiles of all
stations revealed a sharp, seasonal thermocline beneath the shallow, surface
mixed layer. Although temperatures were relatively constant (between 11 and
14°C) over the depth range between 50 and 150 m, large variations were
observed between 25 and 50 m. The most extreme temperature variation was at .
Station 4, where an isothermal layer of 8°C-water was observed between 30 and
40 m.
The middle panel of Figure B-2 illustrates that salinities at Station 4
were also relatively low within this isothermal layer (between 30 and 40 m).
This specific water type (8°C, 33.2 ppt) is normally associated with a well-
known east coast hydrographic feature named the "cold pool." This water mass
obtains its properties during late winter when the mixed layer at the edge of
the continental shelf is relatively cool and fresh. As the surface waters
warm during spring and summer, the lower portion of this water mass (the
prior winter's mixed-layer) becomes isolated from the surface, and its
properties remain uncianged for many months.
B-l
-------
39 10'N
39' O'N
2* 30'N
73 3' H
n 43- x
29' M
78' 3- H
FIGURE B-l.
LOCATIONS OF CTD PROFILE STATIONS OCCUPIED ALONG THE EASTBOUND
TRANSECT TO THE 106-MILE SITE ON AUGUST 31, 1987.
B-2
-------
The cold, fresh layer of "cold pool" water observed at Station 4 appears
to be a small, isolated water parcel because water properties at the
surrounding stations were distinctly different. This isolated parcel of
water may have been attached to a larger parcel extending north or south of
the transect. This theory, however, could not be confirmed by the existing
station data.
The lower panel of Figure B-2 presents a composite of temperature/
salinity (T/S) diagrams from Stations 1, 4, and 5. The highest temperature
of each profile represents the surface properties at each station. This
figure illustrates that the near-surface waters (>15°C) at Station 1 were
significantly fresher than offshore surface waters or, in other words, near-
surface waters at Station 1 were representative of shelf water whereas slope
water was observed at the offshore stations. Note, however, that the layer
of shelf water at Station 1 penetrated to only 25 m and that relatively
saline slope water was found below this depth. Shelf water was observed
within the upper 18 m of the water column at Station 2 but none was found
farther offshore. From this analysis, it appears that the offshore (surface)
boundary of the shelf water was situated approximately 25 nm west of the 106-
Mile Site on August 31, 1987.
The T/S diagrams presented in Figure B-2 also illustrate the extremely
cold, fresh characteristics of the "cold pool" water (8°C, 33.2 ppt) at
Station 4. Beneath this anomalous layer, slope water characteristics are
observed at all three transect stations (1, 4, and 5).
Figure B-3 presents vertical profiles of density (sigma-t), light
transmission (beam attenuation), and dissolved oxygen for the three stations
presented in Figure B-2. Despite the large variability in T/S structure at
the three stations, vertical profiles of sigma-t (top panel) are relatively
similar showing strong vertical density gradients of the seasonal pycnocline
extending from the base of the shallow, surface mixed layer to depths of
roughly 40 m. ' Below this depth, weak vertical gradients are similar at all
stations.
The middle panel of Figure B-3 presents vertical gradients of
transmissometry data, presented in terms of the beam attenuation coefficient,
for Stations 1, 4, and 5. Beam attenuation is linearly proportional to total
suspended solids or turbidity. The Sea Tech transmissometer interfaced to
B-4
-------
50
3 100-
x
ISO-
200-
10
TEMPERATUF1E (C5
15
i 100-
5
a.
150-
200
20-
UJ
!-
UJ
10-
33
SALINITY (PPT)
34
35
25
33
FIGURE B-2.
(MIDDLE);
4
B-3
-------
SIGMA-
FIGURE B-3.
50-
£ 100
I
h-
a.
8
150
200
. 0.0
0-
50-
1 100'
150-
200
50-
£ 100-
x
H-
a
5
150-
200
BEAM ATTENUATION tl/«)
0.2 0.4 0.6 O.S
OXYGEN (1*1/1)
4 6
4\_VI
i.o
COMPOSITE OF HYDROGRAPHIC PROFILE RESULTS FROM STATIONS 1, 4
AND 5: SIGMA-T PROFILES (UPPER); BEAM ATTENUATION PROFILES
(MIDDLE); OXYGEN PROFILES (LOWER).
B-5
-------
the CTD profiling system measured the percent extinction of light along a 25-
cm pathlength, but light extinction (L) is exponentially related to total
suspended solids and is, therefore, misleading for quantitative
interpretations of sludge concentrations. The relationship between the beam
attenuation coefficient (A) and measured light extinction (L) is given by the
expression:
L « e-0.25A
or
A = -4 In L
where L ranges from 0 to 1.0, 0.25 represents the pathlength in meters, and
A is expressed in units of meters-1 (m-1).
The vertical profiles of beam attenuation shown in Figure B-3 exhibit
consistent values within the surface mixed layer and below 50 m but, within
the seasonal pycnocline, a great deal of variability was observed among the
three transect stations. Between 20 and 50 m, beam attenuation was
significantly greater than values above and below the pycnocline, and at the
offshore stations (4 and 5), a very thin (<10 m) layer of relatively high-
beam attenuation was highly pronounced. These high values were associated
with the base of the seasonal pycnocline and, at Station 4, the highest
values were observed at the upper boundary of the "cold pool" water.
Relatively high values of beam attenuation in the seasonal pycnocline
off the U.S. east coast have been observed by other investigators. As part
of the Shelf Edge Exchange Program (SEEP), Churchill et al. (1988) reported
similar values along a cross-slope transect south of New England. The
relatively high beam attenuation values were attributed to natural
particulate matter, but additional sampling and laboratory analyses are
required to ascertain the composition of this material. From the work of
Churchill et al. (1988), it can be determined that beam attenuation values of
0.7 m-1 correspond to suspended particulate concentrations on the order of
0.5 mg/L. These concentrations are low compared to suspended loads in
coastal and shelf waters, but in a water column composed of relatively clear
s'ope *3ter, elevated concentrations of participates are an excellent
B-6
-------
indication of physical and biological processes governing the vertical
transport of particulate material.
Vertical profiles of dissolved oxygen concentration at Stations 1 and 4
are presented in the lower panel of Figure B-3. These profiles illustrate
that mixed-layer oxygen concentrations are on the order of 4.5 ml/1, but
within the seasonal pycnocline (at 20 to 25 m) oxygen concentrations exceed
6 ml/1. These oxygen concentrations represent approximately 110 percent
saturation which is maintained by high biological productivity within the
pycnocline. Below this near-surface oxygen maximum, concentrations at
Station 1 decrease nearly monotonically to 150 m. In contrast, oxygen
concentrations below the pycnocline at Station 4 exhibit large inversions due
to lateral interleaving of water masses. Note, for example, that the oxygen
minimum near 35 m coincides with the cold, fresh water of the "cold pool"
water mass discussed above.' Relatively low oxygen concentrations within the
"cold pool" are consistent with the hypothesis that this water parcel*has
"aged" since contact with the sea surface during the prior winter, and that
biological consumption has significantly reduced its dissolved oxygen
concentration.
It is important to point out that dissolved oxygen concentrations within
and below the seasonal pycnocline at the 106-Mile Site (in summer) are highly
variable due to natural biological processes and water mass advection.
Horizontal variations within the mixed layer may be small, but variations of
0.5 ml/I over horizontal distances of a few kilometers may be expected
beneath the pycnocline. This background variability must be better
understood if estimates are to be made of the depletion of oxygen due to the
discharge of sludge at the 106-Mile Site.
To illustrate the vertical and horizontal variations in hydrographic
properties along the eastbound CTD transect, Figure B-4 presents vertical
sections of temperature (top), salinity (middle), and sigma-t (bottom) along
a line connecting Stations 1 through 6 (see Figure B-l for positions). These
two-dimensional diagrams have been objectively contoured using a spline
function for vertical and horizontal smoothing. Consequently, some of the
most extreme (and thin) property anomalies have been smoothed out, but the
general characteristics of each property field are well represented.
B-7
-------
The temperature section presented in Figure B-3 illustrates the sharp
seasonal thermocline situated between approximately 15 and 30 m. Vertical
temperature gradients vary somewhat across the transects, but the near-
surface thermocline is relatively horizontal across the entire transect. The
only major temperature feature that is evident beneath the thermocline is the
parcel of "cold pool" water situated at 35 m beneath Stations 4 and 5. This
coincides with the low-salinity feature observed in the salinity section
(middle panel) of Figure B-4. In general, salinities increase with depth
over the upper 150 m of the water column in this region. The increase in
near-surface salinities from Station 1 to Station 3 represents the boundary
between shelf and slope waters along the transect.
The lower panel of Figure B-4 presents the two-dimensional density
(sigma-t) field along the eastbound CTD transect. Sharp vertical density
gradients between 15 and 35 m correspond with the seasonal pycnocline;
vertical gradients below this level are much weaker. The density transect
reveals a relatively consistent pycnocline across the entire transect from
Station 1 to Station 6. Only a gradual rise in the pycnocline depth can be
detected from Station 1 to Station 5. If there were no currents in the lower
part of the water column, then the offshore rise of the pycnocline would be
indicative of a southward current within the near-surface layers across the
transect, but additional, wide-area current information would be required to
resolve this current structure. Likewise, deepening of the pycnocline from
Station 5 to Station 6 may represent northward near-surface flow, but a
longer transect would be required to support this assumption. Both the
temperature and density fields do, however, clearly illustrate that a warm-
core Gulf Stream eddy did not occupy the northern portion of the 106-Mile
Site on August 31, 1987. Had an eddy been present, isotherms and isopycnals
would have sloped sharply downward due to the relatively warm and less-dense
waters contained within warm-core eddies.
Figure B-5 presents vertical sections of beam attenuation and dissolved
oxygen similar to those presented in Figure B-4. The upper panel clearly
illustrates that beam attenuation (natural turbidity) is highest within the
seasonal pycnocline (20 to 40 m). Maximum values are observed at Stations 4
and 5, in association with the "cold pool" as discussed previously.
B-8
-------
TEMPERATURE (C)
2. .3 > 5
1 SO
72°S6'W
Uongltud*
71 e 56'W
o .
1 SO
72«36'W
SALINITY (PPT)
Longitud*
71 ° S6'W
1 SO
72°S6'W
7 1 e SS'W
E B-4. VERTICAL TRANSECT OF HYDROGRAPHIC PROPERTIES ALONG EASTBOUND
CTD TRANSEa (SEE FIGURE 4.1 FOR STATION LOCATIONS):
TEMPERATURE (UPPER); SALINITY (MIDDLE); SI6MA-T (LOWER).
B-9
-------
Jj 50
"a- 100
1 50
BEAM ATTENUATION (1/m)
Jl J2 3 > 5 6
72°56'W
Long!tuci<
71°5S'W
J- 100
1 SO
72°56'W
OXYGEN (ml/l)
.3
SS'W
FIGURE B-5.
c °F "YDROSRAPHIC PROPERTIES ALONG EASTBOUND
CTD TRANSECT: BEAM ATTENUATION (UPPER); OXYGEN (LOWER).
B-10
-------
The lower panel of Figure B-5 .presents oxygen data for Stations 1
through 4 and Station 6 (oxygen data are not available from Station 5 due to
a problem with the pump which delivers water to the oxygen sensor of the Sea
Bird CTD system). The highest oxygen concentrations (>6 ml/1) are found
within a thin layer that coincides with the seasonal pycnocline. Horizontal
gradients are rather weak, as observed for the other water properties.
To summarize, the hydrographic data collected along the eastbound CTD
transect to the 106-Mile Site revealed the following background conditions:
All hydrographic observations were typical for summer
conditions at the 106-Mile Site, as deduced by comparison
with past studies along the U.S. East Coast.
A sharp seasonal pycnocline was situated between roughly
20 and 40 m along the entire transect that included the
northern portion of the 106-Mile Site.
The upper 150 m of the water column at the 106-Mile Site
was composed of slope water; only a thin (20 m) layer of
shelf water was observed east (inshore) of 72°40'W
longitude, a distance of 25 nm west of the 106-Mile Site.
Temperature/salinity and oxygen analyses indicated
extensive lateral (isopycnal) mixing of water masses
within and below the seasonal pycnocline.
Natural turbidity levels were highest within the seasonal
pycnocline.
The water column structure and properties in the vicinity
of the 106-Mile Site indicate that a warm-core Gulf Stream
eddy was not present, at least during the first day of the
survey (August 31, 1987).
Water Masses During Plume-Tracking Surveys
Because the primary objective of the hydrographic profiling made during
the individual plume tracking surveys was to acquire data within the sludge
plumes, few hydrographic profiles were made in "clean" background water. It
is, however, informative to look at data from a few stations during each of
the three days of survey operations for the purpose of illustrating the
var-.aDility in background properties'of temperature, salinity, density, and
B-ll
-------
dissolved oxygen. Figure B-6 presents a composite of four density (sigma-t)
profiles, each obtained during one of the four plume tracking surveys (DB-1,
DB-2, DB-3, and DB-4). The individual profiles were separated by roughly 20
h as indicated below:
Survey
DB-1 '
DB-2
DB-3
DB-4
CTD
Profile
1-5
2-1
3-6
4-2
Profile
Depth (m)
59
67
55
56
Date
9-1-87
9-2-87
9-3-87
9-4-87
Time
1710
1556
1140
0639
Figure B-6 illustrates that the depth (thickness) of the surface mixed
layer remained very constant (between 11 and 14 m) over the four days of
surveying. The shape of the seasonal pycnocline varied somewhat but, in
general, strong vertical density gradients were evident between 15 and 35 m.
It will be shown in Section 4.3.3 that initial mixing within the sludge
plumes penetrated to the base of the mixed layer, but the sludge was
apparently less dense than the waters of the seasonal pycnocline and,
consequently, plume waters were not observed below approximately 20 m.
Figure B-7 presents a composite of temperature/salinity (T/S) profiles
from each of the four plume surveys. These profiles demonstrate that near-
surface T/S properties varied greatly during individual plume surveys, as
well as from survey to survey (day to day). Profile depths and times are
given below:
Survey
DB-1
DB-1
DB-2
DB-2
DB-3
DB-3
DB-4
CTD
Profile
1-2
1-6
2-1
2-3
3-1
3-6
Profile
Depth (m)
45
26
67
67
67
55
4-2
56
Date
9-1-87
9-1-87
9-2-87
9-2-87
9-3-87
9-3-87
9-4-87
Time
1407
1732
1556
2054
0816
1140
0639
B-12
-------
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B-13
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B-14
-------
During the first plume survey (DB-1), seven of nine total CTD profiles
exhibited nearly isohaline (constant salinity) properties from the surface to
approximately 40 m (a temperature range from 22 to 10°C). These
characteristics are represented by profile 1-6. Profile 1-2, which was made
a few hours earlier and 4 miles to the south of profile 1-6, had near-surface
salinities that were more than 1 ppt greater than shown by the other
profiles. These high salinities indicate that waters of Gulf Stream origin
resided within the 106-Mile Site on September 1, 1987, most likely as a
result of water that had been advected into the region during the earlier
passage of warm-core eddy "87-E," (Note that the two profiles shown for
survey DB-1 did not extend as deep as those shown for other surveys in Figure
B-8.)
The near-surface T/S profiles obtained during plume survey DB-2
exhibited a similar trend of normal slope water (nearly isohaline from 22 to
8°C) interrupted by subsurface layers of relatively saline Gulf S-tream waters
within the temperature range from 9 to 17°C. The upper right panel of Figure
B-8 illustrates a typical slope water T/S profile (2-1) and a profile with
highly saline waters from 17 to 9°C (2-3). The T/S properties at the surface
and at depths greater than 40 m were, however, the same at both stations.
The L-shaped T/S profile of cast 2-1, having temperature and salinity minima
near 8°C, is typical of slope water characteristics during summer.
The T/S characteristics during plume surveys DB-3 and DB-4 (lower panels
of Figure B-7) indicate that, within the upper 60 m of the water column,
slope waters had been displaced by relatively saline waters of Gulf Stream
origin. For survey DB-3, all 16 CTD profiles had T/S properties that were
bracketed by the properties of the two profiles shown (3-1 and 3-6). The
temperature and salinity minima of the slope water were clearly absent, and
the highest salinities were observed near 16°C, similar to profile 2-3 made
during survey DB-2. Only one CTD profile (No. 4-2) to a depth of 50 m was
obtained during survey DB-4, but it also had T/S characteristics similar to
those of survey DB-3.
These T/S results illustrate that, during the 4-day period from
September 1 through 4, 1987, near-surface waters of Gulf Stream origin
entered the northern portion of the 106-Mile Site, probably as a result of .
B-15
-------
warm-core eddy "87-E" that was situated southeast of the site and presumably
moving toward the southwest.
Although the T/S properties of the upper 50 m of the water column at the
106-Mile Site varied greatly during the 4-day survey, temporal variations in
the dissolved oxygen profile were small, as had been observed for density
(sigma-t) profiles shown in Figure B-6. For example, Figure B-8 presents
vertical profiles of oxygen and percent oxygen saturation for profile 1-1 of
survey DB-1 and for profile 3-6 of survey DB-3. Small variations can be
observed in the thickness of the subsurface oxygen maximum (near 20 m
depth), but oxygen concentrations above and below this level were very
similar. Oxygen characteristics of the other 28 CJD profiles made during the
four-day survey were very similar to those shown in Figure B-8.
Profiles of percent oxygen saturation, calculated from the equation of
Weiss (1970), are shown in the two right panels of Figure B-8. For these and
other profiles, surface oxygen concentrations were roughly 90 percent
saturated, whereas, at the depth of the subsurface oxygen maximum, saturation
values exceeded 110 percent. This is a common feature within the seasonal
pycnocline of the slope water and the entire northwestern Atlantic during
summer. The high oxygen concentrations are simply a result of exceptionally
high photosynthetic productivity within the nutrient-rich seasonal
pycnocline.
B-16
-------
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B-17
-------
-------
-------
APPENDIX C
BACKGROUND DATA
III: '
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C-l
-------
TABLE C-2. BACKGROUND WATER QUALITY C.oerfrinoens
ANALYSES, 106-MILE SITE, SE
m Time
Plume
Sample
ID
" i in
AAD855
AAD855
AAD855
AAD856
AAD856
AAD856
AAD857
AAD857
AAD857
AAD859
AAD859
AAD859
AAD874
AAD874
AAD874
AAD879
AAD879
AAD879
AAD883
AAD883
AAD883
AAD884
AAD884
AAD884
AAD916
AAD916
AAD916
AAD917
AAD917
AAD917
AAD918
AA0918
AAD918
«i LCI
or Rep. Depth Start T=0
Event No. (m) Time (h)
"^
S-8
S-8
S-8
S-8
S-8
S-8
DB-1
DB-1
DB-1
DB-1
DB-1
DB-1
DB-2
DB-2
DB-2
DB-2
DB-2
DB-2
DB-2
DB-2
DB-2
DB-3
DB-3
DB-3
DB-4
DB-4
DB-4
DB-4
DB-4
DB-4
DB-4
DB-4
DB-4
1
2
3
1
2
3
1
2
3
1
2
3
1
2
3
1
2
3
1
2
3
1
2
3
1
2
3
1
2
3
1
2
3
6.0
6.0
6.0
41.0
41.0
41.0
6.0
6.0
6.0
33.0
33.0
33.0
6.0
6.0
6.0
20.4
20.4
20.4
24.0
24.0
24.0
6.0
6.0
6.0
6.0
6.0
6.0
12.0
12.0
12.0
19.1
19.1
19.1
2119
2119
2119
2048
2048
2048
0758
0758
0758
0826
0826
0826
0752
0752
0752
2108
2108,
2108
2118
2118
2118
0839
0839
0839
0640
0640
0640
0650
0650
0650
0701
0701
0701
NA
NA
NA
i in
NA
NA
NA
-8.83
-8.83
-8.83
-8.37
-8.37
-8.37
-2.58
-2.58
-2.58
a
a
-2.53
-2.53
-2.53
h
kJ
h
LJ
h
LJ
b
b
b
b
LJ
b
b
C. perfrinoens
(Counts/100 mL)
0.00
0,
0,
0.
00
00
00
0.00
0,
0.
0.
00
00
00
0.00'
0,
0,
00
00
0.00
17.94
29.31
82.94
1.31
5.13
9.31
4.81
.44
.63
1,
5.
1.44
1.38
1.06
0.00
0.00
0.00
0,
0,
06
13
0.06
0.00
0.13
0.00
JIntitial Sampling For Plume DB-2
Dinit^al Sampling For Plumes DB-3 and DB-4.
C-3
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-------
TABLE C-5. BACKGROUND HATER QUALITY PESTICIDE ANALYSES,
106-MILE SITE, SEPTEMBER 1987
Event
S8
S8
DB-2
DB-2
DB-2
DB-2
DB-2
DB-2
DB-3
DB-3
DB-3
Depth
()
6.0
6.0
6.0
6.0
6.0
24.5
24.5
24.5
6.0
6.0-
6.0
Rep.
No.
1
2
1
2
3
1
2
3
1
2
3
Time
After
T=0
BKG
BKG
BKG
BKG
BKG
BKG
BKG
BKG
BKG
BKG
BKG
a-BHC
0.068
-
1.10
1.05
1.24
1.15
0.26
0.16
3.41
9.41
2.20
7-BHC
0.046 .
-
0.65
0.47
0.72
0.99
0.46
0.31
1.74
2.52
1.22
BKG denotes background samples.
Compounds not found: heptachlor, aldn'n, heptachlor epoxide,
cc-endosulfan, dieldrin, p,p'-DDE, endrin aldehyde,
^-endosulfan sulfate, p,p'-DDD, endrin, endosulfan,
p.p'-DDT,
C-6
-------
TABLE C-6. CONCENTRATION OF PCBs FOUND AT BACKGROUND STATIONS
AT THE 106-MILE SITE, SEPTEMBER 1987 (ng/L)
Plume
S8
S8
DB-2
DB-2
DB-2
DB-2
DB-2 .
DB-2
DB-3
DB-3
DB-3
Depth
(»)
6.0
6.0
6.0
6.0
6.0
24.5
24.5
24.5
6.0
6.0
6.0
Rep.
No.
1
2
1
2
3
1
2
3
1
2
3
Time After
T=0 (h)
BKG
BKG
BKG
BKG
BKG
BKG
BKG,
BKG
BKG
BKG
BKG
Clg(206)
-
^,
~
-
0.035
_
0.027
0.055
0.066
0.062
Compounds not found: Cl2(08), Cl3(18), Cl3(18), CU(52), Cl4(44), CU(66),
ClsUOl), Cl5(118), Cl6(153), Cl5(105), Cle(138)f Cl6(187), Cl6(128),
Cl7(180), Cl7(170), Cl8(195)
C-7
-------
-------
APPENDIX D
SUMMARY OF LABORATORY ANALYSES FOR DUMPING EVENTS
DB-1, DB-2, AND DB-3, 106-MILE SITE, SEPTEMBER 1987
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D-6
-------
TABLE D-5. C. perfn'nqens RESULTS FOR SAMPLES
COLLECTED IN SEWAGE PLUME DB-1 AT THE
106-MILE SITE DURING SEPTEMBER 1987
Sample
ID
AAD869
AAD869
AAD869
AAD870
AAD870
AAD870
AAD866
AAD866
AAD866
AAD871
AAD871
AAD871
AA0876
AAD876
AAD876
AAD858
AAD858
AAD858
AAD867
AAD867
AAD867
AAD872
AAD872
AAD872
AAD877
Plume
or
Event
DB1
D81
DB1
DB1
DB1
DB1
DB1
DB1
DB1
DB1
DB1
DB1
DB1
DB1
DB1
DB1
DE
DB1
DB1
DB1
DB1
DB1
DB1
DB1
DB1
Rep.
No.
1
2
3
1
2
3
1
2
3
1
2
3
1
2
3
1
2
3
1
2
3
1
2
3
1
Depth
(ra)
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
19.4
19.4
19.4
21.8
21.8
21.8
22.3
22.3
22.3
20.3
Start
Time
1648
1648
1648
1702
1702
1702
1738
1738
1738
1823
1823
1823
1941
1941
1941
0818
0818
0818
1740
1740
1740
1826
1826
1826
1950
Time
After
T-0
(h)
0.00
0.00
0.00
0.23
0.23
0.23
0.83
0.83
0.83
1.55
1.55
1.55
2.88
2.88
2.88
-8.50
-8.50
-8.50
0.87
0.87
0.87
1.60
1.60
1.60
3.03
c.
perfn'nqens
(Counts/
100 mL)
TNTC
TNTC
TNTC
TNTC
TNTC
TNTC
TNTC
TNTC
TNTC
TNTC
TNTC
TNTC
TNTC
TNTC
361.00
0.00
0.00
0.00
87.38
17.56
26.94
3.06
3.00
3.81
33.19
TNTC= Too Numerous To Count
D-7
-------
TABLE D-6. C. perfringens RESULTS FOR SAMPLES
COLLECTED IN SEWAGE PLUME DB-2 AT THE
106-MILE SITE DURING SEPTEMBER 1987
Sample
ID
AAD878
AAD878
AAD878
AAD881
AAD881
AAD881
AAD882
AAD882
AAD882
AAD880
AAD880
AAD880
Plume
or
Event
DB-2
DB-2
DB-2
DB-2
DB-2
DB-2
DB-2
DB-2
DB-2
DB-2
DB-2
DB-2
Rep
No.
1
2
3
1
2
3
1
2
3
1
2
3
Depth
(«)
6.0
6.0
6.0
6.0
6.0
6.0
10.7
10.7
10.7
34.0
34.0
34.0
Start
Time
1027
1027
1027
1445
1445
1445
1742
1742
1742
1927
1927
1927
Tine
After
T=0
(h)
0.00
0.00
0.00
4.30
4.30
4.30
7.25
7.25
7.25
9.00
9.00
9.00
C.
perfrTngens
(Counts/
100 *L)
TNTC
207.00
TNTC
292.00
71.17
43.56
201.44
265.44
299.75
6.56
16.00
5.25
TNTC Too Numerous To Count.
D-8
-------
TABLE D-7. C. perfringens RESULTS FOR SAMPLES
COLLECTED IN SEWAGE PLUME DB-3 AT
THE 106-MILE DEEPWATER DUMPSITE
DURING SEPTEMBER 1987
Sample
ID
AAD885
AAD885
AAD885
AAD886
AAD886
AAD886
AAD900
AAD900
AAD900
AAD891
AAD891
AAD891
AAD892
AAD892
AAD892
AAD904
AAD904
AAD904
AAD908
AAD908
AAD908
AAD909
AAD909
AAD909
AAD898
AAD898
AAD898
AAD887
AAD887
AAD887
AAD889
AAD889
AAD889
AAD893
AAD893
AAD893
AAD899
AAD899
AAD899
Plume
or
Event
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
Rep
No.
1
2
3
1
2
3
1
2
3
1
2
3
1
2
3
1
2
3
1
2
3
1
2
3
1
2
3
1
2
3
1
2
3
1
2
3
1
2
3
Depth
(m)
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
5.0
6.0
6.0
10.4
10.4
10.4
10.7
10.7
10.7
20.0
20.0
20.0
20.6
20.6
20.6
20.1
20.1
20.1
20.7
20.7
20.7
Start
Time
1111
1111
1111
1130
1130
1130
1147
1147
1147
1211
1211
1211
1311
1311
1311
1415
1416
1416
1522
1522
1522
1532
1532
1532
1431
1431
1431
1148
1148
1148
1222
1222
1222
1326
1326
1326
1418
1418
1418
Time
After
T=0
(h)
0.00
0.00
0.00
0.32
0.32
0.32
0.60
0.60
0.60
1.00
1.00
1.00
2.00
2.00
2.00
3.08
3.08
3.08
4.18
4.18
4.18
4.35
4.35
4.35
3.33
3.33
3.33
0.62
0.62
0.62
1.18
1.18
1.18
2.25
2.25
2.25
3.12
3.12
3.12
C.
perfrTngens
(Counts/
100 ml)
16.13
0.44
257.00
231.00
166.00
187.00
62.33
171.00 .
TNTC
121.00
100.00
80.00
TNTC
43.40
27.00
20.00
4.25
33.94.
153.00
149.00
140.00
0.25
4.56
21.38
83.67
280.00
133.00
0.81
0.88
1.06
1.63
1.75
1.13
4.00
69.67
29.31
21.25
22.00
2.88
D-9
-------
TABLE D-7. (Continued)
Sample
ID
AAD910
AAD910
AAD910
AAD890
AAD890
AAD890
AAD894
AAD894
AAD894
Plume
or
Event
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
DB-3
Rep
No.
1
2
3
1
2
3
1
2
3
Depth
(»)
20.2
20.2
20.2
35.8
35.8
35.8
33.2
33.2
33.2
Start
Time
1525
1525
1525
1233
1233
1233
1314
1314
1314
Time C.
After perfrTngens
T=0 (Counts/
(h) 100 ml)
4.23
4.23
4.23
1.37
1.37
1.37
2.05
2.05
2.05
0.44
0.31
0.19
2.31
2.19
1.88
52.00
57.67
9.13
TNTC = Too Numerous To Count.
D-10
-------
TABLE D-8. C. perfrinqens RESULTS FOR SAMPLES
COLLECTED IN SEWAGE
106-MILE SITE DURING
Sample
ID
AAD912
AAD912
AAD912
AAD913
AAD913
AAD914
AAD914
AAD914
Plume
or
Event
DB-4
DB-4
DB-4
DB-4
DB-4
DB-4
DB-4
DB-4
Rep
No.
1
2
3
1
2
1
2
3
Depth
6
6
6
6
6
10
10
9
.00
.00
.00
.00
.00
.50
.50
.50
Start
Time
0001
0001
0001
0443
0443
0443
0443
0457
PLUME DB-4 AT THE
SEPTEMBER 1987
Time
After
T=0
(h)
0.00
0.00
0.00
4.72
4.72
4.72
4.72
4.72
C.
perfrTnqens
(Counts/
100 ml)
TNTC
TNTC
110.00
18.88
21.19
11.06
12,75
10.56
TNTC = Too Numerous To Count.
D-ll
-------
TABLE D-9. RESULTS OF TRACER SAMPLES ANALYZED FROM PLUME DB-2,
106-MILE SITE, SEPTEMBER 1987
Depth
(«)
6.0
6.0
6.0
10.7
10.7
10.7
Time
After
T-0
0.0
0.0
0.0
7.25
7.25
7.25
Rep.
No.
1
2
3
1
2
3b
Cu
Gtg/U
14.74
7.87
0.26
1.07
1.88
2.00
Fe*
Ug/U
117.73
58.52
1.24
7.02
16.00
15.85
Pb
G*g/0
3.25
1.61
0-05
0.19
0.38
0.38
Zna
13.37
6.93
0.16
1.90
2.20
2.00
aSamples are blank corrected.
lvalue is an average of duplicate samples.
D-12
-------
TABLE D-10.
RESULTS FROM TRACER SAMPLES ANALYZED FROM PLUME
DB-3, 106-MILE-SITE, SEPTEMBER 1987
Time After
Depth T=0 Rep.
(m) (h) No.
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
6.0
10.7
10.7
10.7
10.9
10.9
10.9
20.0
20.0
20.0
20.1
20.1
20.1
20.2
20.2
20.2
20.5
20.6
20.6
0.00
0.00
0.00
0.32
0.32
0.32
0.60
0.60
0.60
1.00
1.00
1.00
2.00
2.00
2.00
3.08
3.08
3.08
3.33
3.33
3.33
8.40
8.40
8.40
0.62
0.62
0.62
2.25
2.25
2.25
4.23
4.23
4.23
1.18
1.18
1.18
1
2
3
1
2
3
1
2
3
1
2
3b
1
2c
3
' 1
2
3
1
2
3
1
2
3
1
2
3
1
2
3
1
2
3c
1
2
. 3
Cu
(*3/L)
0.14
0.14
50.01
32.27
16.87
19.22
28.65
1.13
0.14
1.90
4.25
14.39
17.00
7.63
5.68
0.19
0.32
0.40
2.62
5.32
6.26
0.62 ,
0.64
0.66
0.16
0.15
0.14
0.20
0.78
0.27
1.06
0.40
0.55
0.14
0.15
0.13
Fe*
G»9/L)
0.56
0.07
295.14
192.89
107.19
122.58
174.10
7.20
0.12
11.05
23.04
92.54
98.21
43.65
38.21
0.81
1.29
1.86
15.46
27.30
33.18
3.19
2.84
3.01
0.54
1.35
0.23
0.60
6.87
2.78
7.53
2.09
2.74
0.25
0.40
0.22
Pb
to/L)
0.02
0.02
51.51
35.71
18.87
22.63
32.45
1.37
0.02
2.05
4.22
16.07
19.78
8.89
7.59
0.09
0.28
0.35
3.29
6.32
11.22
16.38
0.61
0.70
0.31
0.04
0.02
0.07
0.68
0.22
0.98
0.33
0.49
0.03
0.04
0.02
Zna
G*g/U
0.03
0.02
49.16
39.69
16.24
17.92
23.83
1.00
0.04.
1.88
3.91
14.60
16.26
7.59
6.16
0.06
0.17
0.20
4.75
6.02
5.72
4.18
0.52
0.59
0.53
0.37
0.06
0.12
0.91
0.20
1.07
0.37
0.60
0.08
0.10
0.03
D-13
-------
TABLE D-10. (Continued)
Depth
(n)
20.7
20.7
20.7
33.2
33.2
33.2
35.8
35.8
35.8
Time After
T=0
00
3.12
3.12
3.12
2.05
2.05
2.05
1.37
1.37
1.37
Rep.
No.
1
2
3
1
2
3
1
2
3
Cu
0.14
0.18
0.31
0.14
0.26
0.14
0.12
0.11
0.15
Fea
(rt/U
0.67
0.75
1.81
1.66
1.82
1.07
0.55
0.51
0.50
Pb
0.04
0.55
0..21
0.07
0.20
0.05
0.02
0.02
0.02
Zna
0.05
0.06
0.20
0.09
0.20
0.09
0.11
0.04
0.09
^Results are blank corrected.
bA hole was found in the neck of the sample bottle.
cValue is an average of duplicate samples analysis.
D-14
-------
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D-16
-------
TABLE D-13. WATER QUALITY PESTICIDE ANALYSES. DUMPING EVENTS
DB-2 AND DB-3, 106-MILE SITE, SEPTEMBER 1987
Plume
DB-2
DB-2
DB-2
DB-2
DB-2
DB-2
DB-3
DB-3
DB-3
DB-3
DB-3
MBBV=m
Depth
(»)
6.0
6.0
6.0
10.1
10.5
10.3
6.0
6.0
6.0
7.0
5 - 7
ammmmtmeam
Rep.
No.
1
2
3
1
2
3
1
2
3
1
2
OMHBOM
Tine After
T«0 (h)
4.5
4.6
4.7
7.9
8.1
8.3
4.4
4.5
4.7
5.0
5.6
c-BHC
_
*
1.09
1.35
1.37
^
^
7-BHC
1.95
0.73
0.27
w te /
0.32
0.41
1,0
1.59
1.26
0.52
0.493
0,38
mmi^^^^^m
Oieldrin
(ng/L)
0.14
0.16
0.019
-
"" ^ - i sj^as^
p.p'-DDE
0.11
0.16
0.015
-
aMean of two repicate analyses.
-Means Not detected.
Compounds not found: heptachlor, aldrin, heptachlor epoxide,
oc-endosulfan, endn'n aldehyde, ^-endosulfan
sulfate, p.p'-ODD, endn'n, ^-endosulfan,
p.p'-DDT.
0-17
-------
TABLE 0-14. WATER QUALITY PCS ANALYSES, DUMPING EVENTS DB-2 AND DB-3,
106-MILE SITE, SEPTEMBER 1987 (Concentration in ng/L)
Plume
DB-2
DB-2
DB-2
DB-2
DB-2
DB-2
DB-3
DB-3
DB-3
DB-39
DB-3
JMHOBMCE
Depth
()
6.0
6.0
6.0
10.1
10.5
10.3
6.0
6.0
6.0
7.0
5-7
mmatammmtm
Rep.
No.
1
2
3
1
2
3
1
2
3
1
2
MRBMBM
Ti»e
XMh)
4.5
4.6
4.7
7.9
8.1
8.3
4.4
4.5
4.7
5.0
5.6
MBKHmMn
PCS Isomer
CI6U53) C16(138) C17U87) Cl7(180
0.056
0.024
^
-
0.08
0.16 0.12
-
f
0.032
0.048
^^^ i
0.21
OA4
0.02
0.22
0.10
0.08
0.14
) Cl7(l70) Clg(206;
0.026
0.21
"
-
0.21
0.15
0.08
aMean of two replicate analyses.
-Means Not Detected.
Compounds not found: C12(08). Cl3(18)t C13(18), C14(52), C14(44), C14(66),
C15(105), C15(118), C16(128); Cls(195)
D-18
------- |