FINAL REPORT
SUMMER 1988 106-MILE SITE SURVEY
August 22, 1990
U.S. ENVIRONMENTAL PROTECTION AGENCY
Office of Marine and Estuarine Protection
Washington, DC
Prepared Under Contract No. 68-03-3319
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ACKNOWLEDGMENTS
The participation of the following persons from Battelle in the preparation of
this report is acknowledged: D. Shea, C.D. Hunt, R.E. Hillman, P. Dragos, D.A.
Lewis, D.E.. West, and W.G. Steinhauer.
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TABLE OF CONTENTS
1.0 INTRODUCTION ....
2.0 SURVEY OBJECTIVES . . v ......
2.1 NEARFIELD FATE MONITORING . .
2.2 SHORT-TERM EFFECTS MONITORING .......
2.3 FARFIELD FATE MONITORING .
2.4 SUPPORT ACTIVITIES ',
3.0 SAMPLE COLLECTION AND ON-BOARD MEASUREMENTS . . . ,
3.1 SAMPLE COLLECTION .........
3.1.1 Battelle Ocean Sampling System . . . ,
3.1.2 Water Sample Collection in Plumes . .
3.1.3 Farfield and Background Hater Sampling
3.1.4 Sludge Samples from Barges ......
3.1.5 Neuston Samples . .
3.1,6 Samples for Toxicity Tests . . ... .
3.2 PHYSICAL OCEANOGRAPHIC MEASUREMENTS ....'.
3.2.1 Water Column Profiles ...
3.2.2 Current Measurements
3.3 AUXILIARY MEASUREMENTS
3.4 CETACEAN OBSERVATIONS .
4.0 ANALYTICAL METHODS
4.1 TRACE-METAL ANALYSIS IN WATER SAMPLES . .".
4.2 TOTAL SUSPENDED SOLIDS AND PARTICULATE METALS
4.3 ORGANIC COMPOUNDS .
4.4 CLOSTRIDIUM PERFRINGENS
4.5 FISH EGG ABNORMALITIES *
4.6 TOXICITY TESTING ..........!!.".*
4.6.1 Mysid Acute Toxicity Tests
4.6.2 Indigenous Zooplankton Toxicity Tests
4.6.3 Sea Urchin Fertilization Tests . . . .
5.0 OCEANOGRAPHIC CONDITIONS
5.1 WATER MASS CHARACTERISTICS . .
5.1.1 Satellite Imagery . ; . . .
5.1.2 Water Masses -. . "
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TABLE OF CONTENTS (Continued)
5.1.2.1 Horizontal Gradients
5.1.2.2 Vertical Gradients
5.1.3 Hydrographic Conditions.at the 106-Mile Site .
5.2 NEAR-SURFACE CURRENTS
5.2.1 Near-Surface Drifter Results .
5.2.1.1 Visually Tracked Drogues
5.2.1.2 Satellite Tracked ARGOS Drifters . . .
6.0 NEARFIELD FATE OF SEWAGE SLUDGE ...
6.1 BARGE RECORDS AND DUMPING RATES
6.2 ESTIMATES OF PLUME WIDTH AND HORIZONTAL MIXIXNG . . .
6.3 SLUDGE DILUTION RATES
6.3.1 Sludge Characterization Results
6.3.2 Sludge Dilution Based on TSS Data
6.3.3 Sludge Dilution Based on Total Metal Data . .
6.4 WATER QUALITY MEASUREMENTS
6.5 COMPARISON OF RESULTS TO WATER QUALITY CRITERIA . . .
7.0 BIOLOGICAL EFFECTS
7.1 CHLOROPHYL RESULTS
7.2 TOXICITY STUDIES
7.2.1 Results of Mysid Toxicity Tests
7»2.2 Results of Zooplankton Toxicity Tests ....
7.2.3 Results of Sea Urchin Toxicity Tests
7.3 FISH EGG ABNORMALITIES
7.4 ENDANGERED SPECIES
7.5 FLOATABLE DEBRIS
8.0 FARFIELD FATE OF SEWAGE SLUDGE
8.1 SLUDGE TRANSPORT BASED ON TURBIDITY DATA
8.2 CLOSTRIDIUM PERFRINGENS RESULTS
8.3 CHLOROPHYLL A AND PHAEOPHYTIN RESULTS
8.4 TRACE-METAL RESULTS
8.5 ORGANIC CONTAMINANT RESULTS
9.0 CONCLUSIONS
9.1 DISCUSSION OF NULL HYPOTHESES
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TABLE OF CONTENTS (Continued)
9.1.1 Nearfield Fate . . . .
9.1.2 Short-Term Effects
9.1.3 Farfield Fate . .
9.2 EVALUATION OF SLUDGE TRACERS ......
9.2.1 Turbidity Profiles
9.2.2 Trace-Metal Measurements . . . .
9.2.3 Clostridium Perfringens . . . .
9.2.4 Organic Contaminants and Tracers
10.0 REFERENCES
APPENDIX A. Quality Control Data
APPENDIX B. Summary of Field Data
APPENDIX C. Analytical Results . ...
APPENDIX D. Assessment of Cetaceans and Seabirds
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LIST OF TABLES
Page
TABLE 3-1. SUMMARY OF THE TYPES OF HATER SAMPLES COLLECTED
AND ANALYSES PERFORMED FOR THE SEPTEMBER 1988
SURVEY AT THE 106-MILE SITE ...-. . . 8
TABLE 3-2. SUMMARY OF SAMPLING AND TESTING ACTIVITIES ASSOCIATED
WITH SHORT-TERM BIOLOGICAL EFFECTS MONITORING DURING
THE 106-MILE SITE SURVEY, SEPTEMBER 1988 9
TABLE 3-3. MEASUREMENT SPECIFICATIONS FOR CTD SENSORS ...... 18
TABLE .5-1. SUMMARY OF VISUALLY TRACKED MIXED-LAYER
DROGUE MOVEMENTS ....... 42
TABLE 5-2. SUMMARY OF POSITIONS, TIMES, AND DEPTHS FOR THE ARGOS DRIFTERS
DEPLOYED IN THE VICINITY OF THE 106-MILE SITE DURING THE SUMMER
1988 SURVEY 42
TABLE 6-1. SUMMARY OF DUMPING INFORMATION FOR PLUME
STUDIES CONDUCTED DURING SEPTEMBER 1988
SURVEY AT THE 106-MILE SITE 48
TABLE 6-2. RESULTS OF PHYSICAL AND CHEMICAL CHARACTERIZATION
OF SEWAGE SLUDGE FROM BARGES SURVEYED AT THE
106-MILE SITE DURING THE SEPTEMBER 1988 SURVEY .... 56
TABLE 6-3. INITIAL DILUTION ESTIMATES OBTAINED DURING THE
SEPTEMBER 1988 106-MILE SITE SURVEY .......... 57
TABLE 7-1. RESULTS OF MYSID TESTS FOR SAMPLES BG-21
AND DB-21 (4 h) 73
TABLE 7-2. RESULTS OF MYSID TESTS FOR SAMPLES BG-22
AND DB-22, (3.5 h) 75
TABLE 7-3. RESULTS OF MYSID TESTS FOR SAMPLE DB-23 (4 h) ..... 76
TABLE 7-4. RESULTS OF ZOOPLANKTON TESTS FOR SAMPLES BG-21
AND DB-21, (4 h) 77
TABLE 7-5. RESULTS OF ZOOPLANKTON TESTS FOR SAMPLES BG-22
AND DB-22 (3.5 h) . 78
TABLE 7-6. RESULTS OF ZOOPLANKTON TESTS FOR SAMPLE DB-23 (4 h) .... 79
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TABLE 7-7.
TABLE 7-8.
TABLE 7-9.
LIST OF TABLES (Continued)
RESULTS OF SEA URCHIN FERTILIZATION TESTS COMPLETED
FOR THE DB-21 SAMPLE SERIES-AND BACKGROUND SAMPLES
BG-21 AND BG-22
SUMMARY OF OBSERVATIONS.OF MITOTIC FIGURES IN
FISH EGGS COLLECTED AT THE 106-MILE SITE SEPTEMBER 1988
SUMMARY OF FLOATABLE DEBRIS (ABUNDANCES/100 m2) COLLECTED
WITH A NEUSTON NET DURING THE SUMMER 1988 SURVEY AT THE
106-MILE SITE
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LIST OF FIGURES
FIGURE 1-1.
FIGURE 3-1.
FIGURE 3-2.
FIGURE 3-3.
FIGURE 5-1.
FIGURE 5-2.
FIGURE 5-3.
FIGURE 5-4.
FIGURE 5-5.
FIGURE 5-6.
FIGURE 5-7.
.
FIGURE 5-8.
FIGURE 5-9.
FIGURE 5-10.
FIGURE 5-11.
FIGURE 5-12.
FIGURE 6-1.
LOCATION OF THE 106-MILE DEEPWATER MUNICIPAL
SLUDGE SITE . . . . .
LOCATION OF FARFIELD AND BACKGROUND STATIONS FOR
THE SEPTEMBER 1988 SURVEY AT THE 106-MILE SITE . . . .
NEAR-SURFACE DRIFTER (DROUGUE) USED TO MONITOR WATER
CURRENTS DURING PLUME TRACKING STUDIES . . . . . . . .
CONFIGURATION OF THE ARGOS SATELLITE TRACKED DRIFTER .
SATELLITE IMAGERY OF OCEAN FRONTAL DATA FOR
SEPTEMBER 7, 1988 . .
SATELLITE IMAGERY OF OCEAN FRONTAL DATA FOR
SEPTEMBER 20, 1988
VERTICAL PROFILE OF WATER PROPERTIES AT STATION BG-21 .
CONTOUR PLOT OF MIXED-LAYER AVERAGE SALINITY
OVER THE FARFIELD ARRAY
CONTOUR PLOT OF MIXED-LAYER AVERAGE TEMPERATURE OVER
THE FARFIELD ARRAY
VERTICAL PROFILE OF WATER PROPERTIES
FROM FARFIELD TRANSECT A .
VERTICAL PROFILE OF WATER PROPERTIES
FROM FARFIELD TRANSECT B .
VERTICAL PROFILE OF WATER PROPERTIES
FROM FARFIELD TRANSECT C
TRAJECTORIES OF THE VISUALLY TRACKED MIXED-LAYER
DROGUES DEPLOYED DURING THE PLUME TRACKING OPERATIONS .
SHORT-TERM TRAJECTORIES OF THE SATELLITE-
TRACKED MIXED-LAYER DROGUES DEPLOYED DURING
THE PLUME TRACKING OPERATIONS
SHORT-TERM TRAJECTORY OF THE SATELLITE-TRACKED 50-m DROGUE
DEPLOYED DURING THE PLUME TRACKING OPERATIONS .....
LONG-TERM TRAJECTORIES OF THE SATELLITE-TRACKED DROGUES
DEPLOYED DURING THE PLUME TRACKING OPERATIONS .....
LOCATION OF HORIZONTAL PROFILES TAKEN DURING BACKGROUND
SAMPLING AND PLUME TRACKING .....
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LIST OF FIGURES (Continued)
FIGURE 6-2. HORIZONTAL PROFILE OF MIXED-LAYER TURBIDITY (4 m)
DURING PLUME TRACK DB-23 51
FIGURE 6-3. PLUME WIDTH VERSUS TIME FOR PLUME DB-23 52
FIGURE 6-4. PLUME WIDTH VERSUS TIME FOR PLUME EVENTS MONITORED IN
SEPTEMBER 1987 (DB-1, DB-2. DB-3, DB-4), MARCH 1988
(DB-10). AND SEPTEMBER 1988 (DB-21 AND DB-23) 53
FIGURE 6-5. CONCENTRATION OF TSS IN THE PLUME VERSUS TIME FOR
PLUMES DB-21. DB-22. AND DB-23 53
FIGURE 6-6. SLUDGE DILUTION RATES BASED ON MEASURED
TSS CONCENTRATIONS 59
FIGURE 6-7. SLUDGE PLUME DILUTION CURVES BASED ON MEASURED
TOTAL METAL CONCENTRATIONS 61
FIGURE 6-8. PLOTS OF TOTAL CU. CD. AND PB VERSUS TOTAL FE IN SAMPLES
COLLECTED FROM PLUMES DB-21. DB-22, AND DB-23 63
FIGURE 6-9. PLOTS OF TOTAL ZN. NI. AND TSS VERSUS TOTAL FE IN SAMPLES
COLLECTED FROM PLUMES DB-21. DB-22. AND DB-23 ..... 64
FIGURE 6-10. CONCENTRATION OF AMMONIA AND pH VALUES MEASURED AT BACKGROUND
STATIONS AND DURING PLUME TRACKING OF DB-21 66
FIGURE 6-11. CONCENTRATION OF AMMONIA AND pH VALUES MEASURED AT BACKGROUND
STATIONS AND DURING PLUME TRACKING OF DB-22 67
FIGURE 6-12. CONCENTRATION OF AMMONIA AND pH VALUES-MEASURED AT BACKGROUND
STATIONS AND DURING PLUME TRACKING OF DB-23 68
FIGURE 6-13. PLOTS OF COPPER CONCENTRATIONS IN THE SLUDGE PLUME VERSUS
TIME FOR PLUMES DB-21, DB-22, AND DB-23 70
FIGURE 7-1. RESULTS FROM SEA URCHIN FERTILIZATION TESTS OF DB-21 PLUME
AT 0, 1, 3, AND 4 h AFTER DISCHARGE OF SLUDGE 81
FIGURE 8-1. CONTOUR PLOT OF THE SHALLOW PARTICLE MAXIMUM (PERCENT TURBIDITY)
FIGURE 8-2. CONTOUR PLOT OF CHLOROPHYLL a AT THE SHALLOW PARTICLE MAXIMUM
ON THE FARFIELD TRANSECTS 39
FIGURE 8-3. CONTOUR PLOT OF PHAEOPHYTIN AT THE SHALLOW PARTICLE MAXIMUM
ON THE FARFIELD TRANSECTS gg
FIGURE 8-4. CONCENTRATION OF COPPER AT THE SHALLOW PARTICLE MAXIMUM FOR
FARFIELD TRANSECT A (FA) AND BACKGROUND STATIONS (BG) . 92
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LIST OF FIGURES (Continued)
FIGURE 8-5.
FIGURE 8-6.
FIGURE 8-7.
FIGURE 8-8.
FIGURE 8-9.
FIGURE 8-10.
FIGURE 8-11.
Paqe
CONCENTRATION OF LEAD AT THE SHALLOW PARTICLE MAXIMUM FOR ~~^
FARFIELD TRANSECT A (FA) AND BACKGROUND STATIONS (BG) . 93
CONCENTRATION OF IRON AT THE SHALLOW PARTICLE MAXIMUM FOR
FARFIELD TRANSECT A (FA) AND BACKGROUND STATIONS (BG) . 94
CONCENTRATION OF LEAD AT THE SHALLOW PARTICLE MAXIMUM FOR
FARFIELD TRANSECT B (FB) AND BACKGROUND STATIONS (BG) . 95
CONCENTRATION OF COPPER AT THE SHALLOW PARTICLE MAXIMUM FOR
FARFIELD TRANSECT C (FC) AND BACKGROUND STATIONS (BG) . 96
CONCENTRATION OF LEAD AT THE SHALLOW PARTICLE MAXIMUM FOR
FARFIELD TRANSECT C (FC) AND BACKGROUND STATIONS (BG) . 97
CONCENTRATION OF IRON AT THE SHALLOW PARTICLE MAXIMUM FOR
FARFIELD TRANSECT C (FC) AND BACKGROUND STATIONS (BG) . 98
CONTOUR PLOT OF DISSOLVED LEAD AT THE SHALLOW PARTICLE
MAXIMUM ON THE FARFIELD TRANSECTS 99
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1.0 INTRODUCTION
The United States, Environmental Protection Agency (EPA), under the Marine
Protection, Research, and Sanctuaries Act of 1972, is responsible for
regulating disposal of sewage sludge in U.S. territorial waters. This
responsibility includes developing and implementing effective monitoring
programs to assess compliance with permit conditions and to evaluate potential
impacts on the marine environment. Ocean disposal of sewage sludge currently
is permitted at the 106-Mile Deepwater Municipal Sludge Site (106-Mile Site),
located off the coasts of New York and New Jersey (Figure 1-1). The EPA
monitoring program for the 106-Mile Site ( EPA , 1992a) is being
implemented according to a four-tiered approach ( EPA , 1992b) whereby data
generated in one tier may be used in making management decisions about
continued site designation, awarding of dumping permits, and the design and
implementation of future surveys.
Tier 1 of the monitoring program, Sludge Characteristics and Disposal
Operations, addresses sludge monitoring and assessment to verify that
conditions specified by dumping permits are met and continue to be adequate
during the period of site designation and active disposal. Tier 2 of the
monitoring program, Nearfield Fate and Short-Term Effects, addresses permit
compliance and impact assessment. Permits for disposal of sludges at the site
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.
Monitoring the behavior and movement of sludge immediately after disposal is
also necessary to confirm the assumptions regarding dispersion and dilution
that were made in issuing permits. Tier 3, Farfield Fate, is designed to
determine the transport and fate of the sludge dumped at the 106-Mile Site in
areas outside the 106-Mile Site boundaries. Tier 4, Long-Term Effects, is
designed to determine if long-term biological impacts result from sludge
disposal at the 106-Mile Site.
EPA conducted surveys at the 106-Mile Site in September 1987 and in March 1988
to examine the nearfield fate of the sludge plumes at the 106-Mile Site
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40°N
39°N
38°N
106-Mile Deepwoter
Municipo! SI udge Site
I
76°W 75°W 74°W 73°W 72°W 7I°W
FIGURE 1-1. LOCATION OF THE 106-MILE DEEPWATER MUNICIPAL SLUDGE SITE,
2
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( EPA , 1992c and 1988b). These studies tested methods for tracking sludge
plumes and assessed the behavior and transport of sludge plumes under summer
and winter conditions, respectively. A third survey to the site was made in
September .1988 under Work Assignment 1-U8 (EPA Contract No. 68-03-3319) to
perform Tier 2 (nearfield fate and short-term effects) and Tier 3 (farfield
fate) activities. This survey included plume-tracking studies similar to
those performed previously ( EPA , 1992c and 1988b) to further define the
behavior of sludge plumes.
The September 1988 survey was carried out from September 10 to 20, 1988,
aboard the EPA Ocean Survey Vessel Peter tf. Anderson (OSV Anderson) under the
guidelines of the August 25, 1988, "Final Survey Plan for Summer 1988
Oceanographic Survey to the 106-Mile Site" ( EPA , 1988c). A description
of the survey activities is presented in the Initial Survey Report for "Summer
1988 Oceanographic Survey to the 106-Mile Site" ( EPA , 1988d).
This report describes the activities associated with the September 1988
survey, presents the results of laboratory analyses completed in October 1989,
and provides interpretation of these results as they relate to nearfield and
farfield fate and short-term effects of sewage sludge dumped at the 106-Mile
Site under summer conditions. The specific objectives of the survey are given
in Section 2. The sample-collection methods and onboard measurements are
described in Section 3. The laboratory methods are.discussed in Section 4.
The physical Oceanographic conditions are described in Section 5. Results
from the nearfield fate, short-term effects, and farfield fate studies are
presented and discussed in Sections 6, 7, and 8, respectively. The
conclusions of the study are presented in Section 9.
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2.0 SURVEY OBJECTIVES
The general objectives of the survey were to determine the short-term effects
and evaluate the nearfield and farfield fate of sewage sludge plumes at the
106-Mile Site under summer conditions. Nearfield fate monitoring on the
survey was conducted to verify and refine sludge dilution calculations, thus
addressing permit-compliance issues. Short-term effects were monitored to
address the potential for impacts within the 106-Mile Site during the first
day following a dumping event. Farfield fate studies were conducted to
determine where the sludge goes upon leaving the site and, in particular,
whether the sludge accumulates in the pycnocline.
2.1 NEARFIELD FATE MONITORING
Nearfield fate monitoring on the September 1988 survey addressed the short-
term (<10 h) dispersion and transport of sludge plumes within the 106-Mile
Site boundaries. Specific nearfield fate monitoring objectives, keyed to null
hypotheses presented in the 106-Mile Site monitoring plan ( EPA , 1992a),
were to
• Determine the concentration of sludge and sludge constituents in
sludge plumes outside site boundaries if sludge plumes are observed
to cross site boundaries
• Determine the concentration of sludge and sludge constituents in
sludge plumes within site boundaries 4 h after sludge disposal
. Measure the vertical dispersion of sludge to determine whether
sludge settles below the seasonal pycnocline during summer
conditions
• Monitor the concentration of contaminants for which there are marine
water quality criteria (WQC) in sludge plumes to determine if WQC
are being exceeded 4 h after disposal, or if they are being exceeded
outside the site at any time.
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2.2 SHORT-TERM EFFECTS MONITORING
The objectives of the short-term effects studies on the September 1988 survey
were to _ -
• Assess potential changes in primary productivity at and near the
106-Mile Site through measurement of chlorophyll a and phaeophytin
• Determine the acute and short-term chronic toxicity of seawater
contaminated with sewage sludge
« Assess potential changes in fish populations at the 106-Mile Site by
examining of fish eggs collected at the site for genetic mutations and
other developmental abnormalities
• Determine the potential for sludge contaminants to concentrate in the
marine microlayer
. Determine whether or not sludge dumping has a significant impact on
dissolved oxygen content or pH of the seawater in the area.
2.3 FARFIELD FATE MONITORING
Farfield fate monitoring on the survey assessed the potential of sludge to
impact areas and marine resources outside the site boundaries. The objectives
of farfield fate monitoring on the September 1988 survey were to
. Assess the horizontal transport of sludge into the farfield by mappinq
turbid areas outside the 106-Mile Site (up to 15 nmi) and by measurinq
selected sludge tracers at the particle maxima..
• Evaluate the potential for recirculation of sludge through the 106-
Mile Site and for transporting sludge toward the continental shelf
(and adjacent shoreline, beach, marine sanctuary, fishery, or
shellfishery areas) by monitoring the movement of water masses at the
site.
2.4 SUPPORT ACTIVITIES
To meet the survey objectives, additional activities were required both on
board the survey vessel and on shore. These activities included "
. Collection of sludge samples from barges dumping at the site for
analysis of selected sludge constituents to allow accurate calculation
of sludge dilution
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Acquisition of satellite-derived ocean frontal analyses; determination
of conductivity, temperature, oxygen, and depth profiles; and
measurements of current shear to determine oceanographic conditions at
the site that could, affect the movement of the sludge
Acquisition of real-time navigation data to support plume-tracking
activities
Observations of endangered species of cetaceans, marine turtles, and
seabirds, according to EPA policy, to record observations of these
animals on all surveys to the 106-Mile Site.
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3.0 SAMPLE COLLECTION AND ON-BOARD MEASURMENTS
Sample collection and processing procedures were similar to those followed on
previous surveys (EPA, 1988b, 1992c); they have been described in detail in
the survey plan ( EPA , 1988c). Brief descriptions of these procedures and
deviations from the survey plan are given below. A description of the samples
collected on the survey is given in the Initial Survey Report ( EPA
1988d). A summary of the types of samples collected and analyses performed is
given in Table 3-1. A summary of sampling and on-board testing activities for
short-term biological effects monitoring is given in Table 3-2. All samples
were transferred to the analytical laboratory at Battelle Ocean Sciences
(Battelle) under strict change-of-custody procedures.
3.1 SAMPLE COLLECTION
3.1.1 BatteHe Ocean Sampling System
Water column sample collections during both the nearfield and farfield
monitoring phases of the survey were conducted by using the Battelle Ocean
Sampling System (BOSS). The BOSS contains a Sea-Bird Inc., high-resolution
conductivity/temperature/depth (CTD) profiling system that is attached to a
weighted delta-fin depressor. The depressor allows the unit to be towed
horizontally at speeds up to 4 kn or to be (ised in a vertical profiling mode.
The BOSS also houses sensors for determining dissolved oxygen and a 25-cm-
pathlength SeaTech transmissometer for determining turbidity. All data are
acquired by an on-board computer and stored on diskette.
In addition to the in situ sensors, the BOSS is equipped with a custom-built
seawater pump connected to the ship's laboratory with a Teflon® tube that is
enclosed in the electromechanical ;cable attaching the sensor package to the
data handling system. The pump drivers water to the on-board laboratory at a
minimum rate of 14 L/min. I .,
The BOSS was also connected throu
navigation system. This system w
ha computer interface to a Loran-C
s used to determine the position of the
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TABLE 3-1. SUMMARY OF THE TYPES OF WATER SAMPLES COLLECTED AND ANALYSES
PERFORMED FOR THE SEPTEMBER 1988 SURVEY AT THE 106-MILE SITE,
Parameter
Place of Analysis
Nearfield
Survey
Farfield
Survey
Trace metals
Organic compounds
Total suspended solids
Clostridium perfringens
Ammonia
PH
Chlorophyll cr/phaeophytin
Toxicity tests
Batten ea
•• NAb
Battelle
NCC
OSV Anderson
OSV Anderson
OSV Anderson
OSV Anderson
Battelle
Battelle
Battelle
Battelle
NC
NC-
OS V Anderson
NC
* Battelle: Duxbury, MA.
D NA: Not analyzed.
c NC: Not collected.
8
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vessel during all sample-collection operations. During survey operations, the
depth, salinity, temperature, and turbidity data acquired during either
horizontal towing or vertical profiling operations were graphically displayed
in real time on a color monitor. Hard copies of the data were plotted as the
data were acquired.
Both the horizontal and vertical profiling capability of the BOSS were used
during the survey. Horizontal towing was performed primarily during nearfield
monitoring exercises. The vertical sample collection mode was employed during
the farfield and background station sample collection exercises. The location
of sample positions within the sewage-sludge plumes and in the pyenocline was
determined from real-time turbidity measurements by using an in situ
tramsmissometer on the BOSS.
3.1.2 Hater Sample Collection In Plumes
During horizontal towing operations, the real-time depth and turbidity data
were used to identify the location (depth and horizontal width) of the
particle maximum in the sludge plumes as the survey vessel crossed the plume
axis. Horizontal towing operations were conducted near the surface drogue
used to mark the initial sampling (TQ) of the plume. The procedures used to
mark the sampling location in the plume were identical to those used on
previous surveys of sewage sludge plumes at the 106-Mile Site ( EPA , 1992c
1988b ) and were based on the location of the particle maximum. Samples were
collected when the BOSS was raised and located within the identified particle
maximum. After this initial sample collection, the vessel resumed horizontal
towing operations.
During the first hour after sludge disposal, the depth of sludge penetration
in the surface waters, the horizontal extent of the plume, and the width of
the maximum concentration of sludge in the plume were determined from numerous
horizontal transects of the plume. Based on this information, the"depth of
the highest particle concentrations was identified and the BOSS was set at
that depth to collect water samples in the plume. Samples from the BOSS pump
outlet were collected about 1.3 min after reaching the particle maximum to
10
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account for the residence time of water in the piping system. This technique
allowed relatively easy and accurate collection of water samples from the
plume particle maximum.
During this operation, five types of samples were collected: 1 L for trace-
metal analysis, 4 L for water quality analysis (ammonia, pH, chlorophyll a
and phaeophytin), 1 L for total suspended solids, 4 L for analysis of organic
tracer compounds, and 3 L for toxicity tests. In most cases, these samples
were collected in duplicate. Samples for the most critical parameters, metals
and acute toxicity, were collected in parallel by using the dual sample-
collection ports on the BOSS. The second set of sample duplicates was
collected sequentially after all samples from the first set of duplicates had
been collected. Most sample collections were completed in less than 2 min
Shipboard analysis of ammonia and pH were performed within 1 h of sample
collection.
Total metal samples collected during nearfield plume studies were collected in
acid-cleaned polyethylene bottles and acidified (to pH < 2) with HNOo
immediately after collection. Samples for total suspended solids (TSS) were
vacuum-filtered through acid-cleaned 47-mm 0.4-^m Nuclepore filters The
volume.that was filtered was measured by using volumetric cylinders Filter
samples were stored in cleaned, sealed polycarbonate petri dishes. Samples
for organic -contaminants were preserved with 120 ml_,of dichloromethane (DCM).
3.1.3 Farfield and Background Water Column Sampling
The locations of the farfield and background sample stations are indicated in
Figure 3-1. Water samples were collected after a CTD hydrocast was conducted
From each hydrocast, the major oceanographic features in the upper 50 m of the
water column were identified. Upon completion of this cast, the depth of the
particle maximum was determined from the turbidity profile. The BOSS was then
positioned in the particle maximum located in the pycnocline and samples were
collected. A second particle maximum located above the pycnocline was
observed at two stations. Duplicate samples for total metal and Clostridium
perfrwgens determinations were collected from several of these paniculate
11
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3S*20'N
33'10'N
33 O'N
3B*50*N
38'40'N
3B 30'N
3B 20'N
FC-6i
FC-5«
Farfield
Transect FC-4
C
FC-3
FC-2
BG22
• BG21
106-Mile Site
FC-1 • FA-1 • I •FB'1
FA-2
Farfield
Transect
A
FA-5
FA-6
FA-7
• FB-2
FA-3»-l •FB-3
FA-4 • • FB-4
Farfield
Transect
B
FB-5
FB-6
FB-7
-,n-10'M I I 1 1 ' > '
72*30' H 72'20' H 72*10' H 72* O1 H 71*50' H 71*40' H 71*30' W
FIGURE 3-1.
STATION LOCATIONS
LOCATION OF FARFIELD AND BACKGROUND STATIONS FOR THE SEPTEMBER
1988 SURVEY AT THE 106-MILE SITE.
12
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maxima to determine if they were related to sludge disposal at the 106-Mile
Site.
During this phase of the study, four sets'of samples were collected: 1 L for
dissolved and particulate trace-metal analysis (total suspended solids were
determined from the particulate trace-metal sample); 4 L for analysis of
ammonium, pH, chlorophyll a. and phaeophytin; 100 L for analysis of organic
tracer compounds (particulate phase only); and 2 L for Clostridium perfringens
analysis. Duplicate samples were collected sequentially. Sample collections
for the small-volume samples (<4 L) were generally completed in Jess than 2
min; collection of duplicate organic samples (100 L) took about 10 min.
Samples for total suspended solids (TSS) and particulate trace-metal
determination were vacuum-filtered through acid-cleaned 47-mm 0.4-/
-------
were refrigerated immediately after collection. Samples for trace metals,
TSS, Clostridium perfringens, and organic compounds were returned to Battelle
for later analysis.
3.1.4 Sludge Samples from Barges
Between September 9 and 18, sewage sludge samples were collected from 11
barges preparing to depart for the 106-Mile Site. Samples were collected from
fully loaded barges or barges completing final loading operations. Sludge
samples were obtained from each barge compartment by using a stainless steel
bomb sampler of 500-mL capacity. Three grab samples from each barge
compartment were collected: one from the upper 2 ft, one from middepth, and
one from 2 ft above the bottom. All grab samples were combined in a large
container (10 L) and stirred to provide a homogenized, composite sample.
Subsamples from this composite were then collected and shipped on Blue Ice® to
the analytical laboratory (Science Applications International Corporation).
All samples were held until the barges monitored at the 106-Mile Site were
identified. Sludge samples from only the three barges monitored at the 106-
Mile Site were analyzed for metal contaminants.
3.1.5 Neuston Samples
Ichthyopjankton and plastic debris samples were collected during horizontal
transects by towing a neuston net (2- x 1-m opening dimensions, 0.3-mm mesh
size) through the sludge plumes at the sea surface. Each sample tow duration
was less than 1 h. Samples were rinsed into the cod end of the net and the
whole sample transferred to a 4-L polyethylene jug and preserved with 10%
buffered formalin. Samples were stored on board during the cruise and then
transferred to Battelle for subsequent analysis of possible chromosome
abnormalities in the developing fish embryos. Collections were made on
September 16 at T = 1 and 3 h; on September 17 at T = 1 and 2 h; and on
September 18 and 19 at T = 0, 1, 2, 3, and 4 h. Background samples were taken
on September 16 and 17 at Station BG-21. A summary of the neuston samples is
given in Table 3-2.
14
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3.1.6 Samples for Toxlcitv Tests
Cultures of test organisms (mysids and sea urchins) were delivered to the OSV
Anderson on September 9 during mobilization for the cruise. The microbiology
laboratory on the OSV Anderson was reorganized for use as a culturing and
toxicity laboratory. Test organisms were held in static-recirculating
aquarium systems, necessitating daily water changes. A summary of the samples
collected for toxicity tests is given in Table 3-2.
Collections of indigenous zooplankton were made by towing a 1-m-dia conical
plankton net (0.5-mm Nitex mesh) for 10 to 20 min just below the. seawater
surface at Background Station BG-20 (39'07'N, 72°05'W). Zooplankton were
rinsed gently into the cod end of the net and then through a series of sieves
for separation into size groups of 4, 1, and 0.5 mm. Copepods retained in the
O.Srmm sieve were transferred in seawater to a plastic tub and delivered to
the testing laboratory. Copepods were examined with a dissecting microscope
and sorted according to apparent likeness in body form, color, and size.
Representative samples of copepods used for testing were preserved in formalin
and returned to Battelle for taxonomic identification.
On September 11, a background sample (B6-20) and sludge plume sample (DB-20)
were collected at T = 0 h from the plume of the barge Sea Trader. However,
the intake bf the sampling device may not have been .within the boundaries of
the plume when this sample was collected and, therefore, tests were not
performed on these samples. Shipboard electrical problems, which developed
during the DB-20 sampling attempts, and unsuitable sea conditions delayed the
scheduled sampling and toxicity tests for several days. During this time,
activities centered on the general maintenance of cultures and the conduct of
preliminary test trials with each test organism. Although sufficient mysids
were available on board for the scheduled toxicity tests, the delay resulted
in aging of the existing mysid culture beyond the optimal age for testing. It
is standard practice to conduct toxicity tests with juvenile mysids;
therefore, a decision was made to ship a new batch of mysids from Battelle.
This shipment was received in Cape May, New Jersey, on September 12.
15
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The first sample received for a full suite of toxicity tests was collected on
September 16 at Background Station BG-21 (Figure 3-1). Later the same day,
plume samples from the Princess B (event DB-21) were collected in the plume at
T - 0, 1, 3, and 4 h after sludge disposa-1. Samples were characterized for
salinity, temperature, pH, and dissolved oxygen immediately upon receipt in
the laboratory. Toxicity tests were initiated on the morning of September 17,
between the hours of 0030 and 0135. Sea urchin fertilization tests were
completed on the T = 4 h sample only. Seawater collected at 38° 51.2'N, 72°
27.0'W on September 16 was used as a control for the toxicity tests. The
control water was stored at room temperature and used to assess the responses
of test organisms to test conditions in uncontaminated seawater. The
background sample (BG-21) was tested concurrently with the DB-21 samples.
On September 17, a collection of zooplankton was made to restock the culture.
Samples were collected for toxicity testing at Background Station BG-22
(Figure 3-1) and in the plume of the barge Spring Creek (DB-22) at T = 0, 1,
2, and 3.5 h. Toxicity tests for these samples were initiated during the
morning of September 18 between the hours of 0030 and 0530.
On September 18 and 19, during the period from 2300 to 0315 h, plume samples
from DB-23 were collected in the discharge plume of the barge Lemon Creek.
Sea urchin fertilization tests and the mysid acute test were initiated on
September 19 between the hours of 0300 and 0600. In-itiation of the
zooplankton test was delayed until the afternoon of September 19, when a new
batch of organisms was collected. Plume sample collection at the 106-Mile
Site was completed with the DB-23 collections on September 19.
The OSV Anderson docked at Woods Hole, Massachusetts, for demobilization on
September 20, and the ongoing acute tests (mysid and zooplankton) were
transferred to Battelle for completion of the test period. All frozen water
samples and ichthyoplankton samples were transferred to Battelle.
16
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3.2 PHYSICAL OCEAN06RAPHIC MEASUREMENTS
Physical oceanographic data were acquired during the survey by vertical and
horizontal..profiling of the water column,.and by deploying near-surface
visually tracked and satellite-tracked drifters. In addition, satellite
images of sea surface temperature for the area were obtained after the survey
was completed.
3.2.1 Hater Column Profiles
Vertical and horizontal water column profiling of physical parameters was
performed by using the BOSS (described in Section 3.1.1).. Measurement
specifications for the sensors on the BOSS are presented in Table 3-3.
Following the survey, binary files of the digital CTD data were returned to
the laboratory for processing and review, including
° $onv«:rs.ion of raw (binary) CTD data into engineering units:
depth (IB), temperature (-C), salinity (ppt), oxygen (mg/L), and light
transmission (% light extinction)
• Removal of data points that exceed instrumental full scale and lie
clearly outside reasonable ranges for each measurement parameter
Electronic transients and sensor contact with suspended material
(e.g., seaweed) cause infrequent (< 1%) full-scale signals and are
removed'.
• Retention of data points only when the depth series is monotonically
increasing (because good quality CTD data can be obtained only when
the sensors are descending through the water column and passinq
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.
17
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TABLE 3-3. MEASUREMENT SPECIFICATIONS FOR CTD SENSORS
Parameter
Depth
Temperature
Salinity
Oxygen
Light transmission
Range
0 to 3000' m
-5° to 35°C
0 to 40 ppt
0 to 15 mg/L
0% to 100%
Accuracy
±60 cm
±0.004°C
±0.005 ppt
±0.1 mg/L
±0.5%
Resolution
12 cm
0.0003°C
0.0005 ppt
0.01 mg/L
0.01%
Sampling rate: 24 samples per second (averaged to 8 samples per-second)
Vertical resolution during profiling: ~4 cm for 20 m/min lowering speed
Horizontal resolution during towing: ~20 cm at 3-kn ship speed
18
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3.2.2 Current Measurements
Near-surface drifters, designed to maximize the cross-sectional area of the
drogue while minimizing the surface area.and windage of the surface marker*
were fabricated for plume-tracking operations. These drifters are similar to
those used in previous plume-tracking, surveys (EPA, 1988b, 1992"I). The
drifters consisted of a subsurface drag body, a 2-m-long section of sheet
metal, suspended 5 m below a small surface float (Figure 3-2). A whip antenna
kept a marker flag aloft and a strobe light was fitted to the whip to provide
visibility at night. To track a plume, the survey vessel crossed the path of
a dumping barge just behind it and, when in the center of the plume, deployed
a drifter. Drifting freely, they marked the location of the plume section
under study.
Drifters were tracked visually from the survey vessel. During horizontal.
profiling, the drifter position was obtained when the vessel passed the
drifter and Loran-C position was recorded on computer diskette. Repeated
transects of the plume were used to define the movement of the drogue.
Four satellite-tracked surface drifters were deployed during the survey to
determine the direction of mean water-mass flow and, therefore, the direction
of sludge transport in the surface waters. These drifters consisted of a
surface float containing a transmitter and a 7.5-m-l
-------
Strobe
Drogue
FIGURE 3-2.
NEAR-SURFACE DRIFTER (DROUGE) USED TO MONITOR WATER CURRENTS
DURING PLUME TRACKING STUDIES. WJKKLHI*
20
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Drogue
Tether
5m. lOm
or 5Om
O
O
O
O
O
O
Surface Float
with Satellite
Transmitter
Holley Sock Drogue
FIGURE 3-3. CONFIGURATION OF THE ARGOS SATELLITE-TRACKED DRIFTER.
21
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positions of significant ocean thermal features such as shelf water, slope
water, the Gulf Stream, and warm-core/cold-core eddies. Following the survey,
the ocean frontal maps for the month of September 1988 were obtained for the
106-Mile Site area.
3.4 CETACEAN 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 according to two major categories: location/
environmental and species/behavior. Information in each category was recorded
for each 15-min observation period and both categories were identified by a
unique survey and observation number. Location/environmental data included
latitude and 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.
22
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4.0 ANALYTICAL METHODS
4.1 TRACE-METAL ANALYSIS IN WATER SAMPLES
Seawater samples for both total and dissolved metal analysis (Cd, Cu, Ni, Fe,
Pb, and Zn) were extracted at pH 5 with a 1% solution of purified ammonium-1-
pyrrolidine dithiocarbamate diethyl ammonium diethyldithiocarbamate (APDC-
ODDC) 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% nitric acid. The nitric acid
solutions were analyzed for Cd, Cu, Ni, Fe, Pb, and Zn via graphite furnace
atomic absorption spectrometry (GFAAS) with Zeeman background correction.
Nickel and Zn were not determined in all samples.
4.2 TOTAL SUSPENDED SOLIDS AND PARTICULATE METALS
Samples for TSS were air-dried in a Class 100 clean room. The TSS
concentration of each sample was determined from the mass of the particles
retained on the filter and the total volume of seawater filtered. After the
mass of the sample on the filters was determined, the filters were digested
for particulate metal determinations. Each filter was placed in a Teflon vial
(20 mL) and digested with 5 mL of 3N nitric acid by sonicating for 1 h. Metal
concentrations (Cd, Cu, Ni, Fe, Pb, and Zn) in the a'cid digestates were
determined via GFAAS by using Zeeman background correction. Potential matrix
interferences were minimized by using a standard curve prepared by the method
of standard additions on one of the particulate samples. Nickel analyses were
performed with the addition of the matrix modifier MgN03; Pb, Cd, and Zn
analyses were performed by using matrix modification with both MgN03 and
NH4H2P04.
4.3 ORGANIC COMPOUNDS
Particulate samples were prepared and analyzed for polynuclear aromatic
hydrocarbons (PAH), linear alky! benzenes (LAB), chlorinated pesticides
(including DDT and its metabolites), and polychlorinated biphenyls (PCB)
23
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following methods established for sediments by the NOAA National Status and
Trends Mussel Watch Program (Battelle, 1988 ). Minor modifications were made
to those methods for the analysis of LAB.
Sample extracts were analyzed by capillary gas chromatography with mass
spectrometry (GC/MS) for PAH and LAB contamination. GC/MS analysis conditions
for LAB were derived from those of Eganhouse et al. (1983). Because the
levels of PAH and LAB in the extracts were in the very low nanogram range, the
mass spectrometer was operated in the selected ion monitoring (SIM) mode to
achieve the lowest possible detection limits. Sample extracts were analyzed
by capillary gas chromatography with electron capture detection (GC/ECD) for
pesticide/PCB content. Any compounds identified in the samples were
quantified by using the method of internal standards. Results are reported in
nanograms per liter of water filtered. Limits of detection (LOD) were
calculated as the concentration of the analyte in the sample producing a
signal five times the backround signal for that sample.
4.4 CLOSTRIDIUM PERFRINGENS
Enumeration of Clostridium perfringens in seawater was performed according to
the methods of Bisson and Cabelli (1979). Clostridium perfringens spores were
collected by filtering aliquots of seawater through 0.4-/
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based on what is known of the spawning periods of fish in the area and on
characteristics of the eggs, such as the size of the egg and the presence,
size, and color of oil droplets in the eggs. The eggs most resembled those of
the Atlantic mackerel, Scomber scombrus...
Determination of chromosomal abnormalities followed the procedures of Longwell
and Hughes (1980) with some modifications. The embryos in each sample were
dissected away from the egg membranes with a fine-point dissecting needle, and
the stage of embryonic development was determined (e.g., morula, blastula,
gastrula). The embryos were placed in a small vial in a 1.5% orcein solution
in 45% acetic acid for 45 min. The stained embryos were^then placed on a
slide, covered with a cover slip, and squashed. From one to six embryos were
able to fit on a slide under a small coverslip. The squashed embryos were
examined with a compound microscope at 400x magnification. The numbers of
each mitotic phase and the numbers of normal and abnormal mitotic figures were
determined.
Several of the eggs contained tail-stage larvae. The larvae were not examined
for abnormalities because of the small amount of material and the relative
lack of mitotic figures at that stage of development.
4.6 TOXICITY TESTING
4.6.1 Mvsid Acute Toxlcitv Tests
Approximately 950 juvenile mysids (Mysidopsis bahia), from the shipment
received in Cape May on September 12, were held in a 2.5-gal aquarium with
aeration to provide water circulation. Water changes and feeding (<24 h post-
hatch Artemia nauplii) were completed twice daily. Salinity, water
temperature, dissolved oxygen, and pH were measured daily. At the time of
test initiation, the ages of test mysids ranged from 5 to 10 days.
Procedures for mysid 96-h acute tests were modified from those outlined in
Peltier and Weber (1985). Ten mysids were exposed to 200 ml of test solution!
for approximately 96 h in a glass 12-oz Ball mason jar. Each sample solution
25
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was tested in triplicate, resulting in a total of about 30 mysids per
treatment. Each test series included a seawater control treatment and a plume
sample collected at T = 4 h. Background samples were tested according to the
same procedures.
Salinity of the sludge plume samples was adjusted from 34 °/oo to 32 °/oo with
deionized water. Mysids in test chambers were fed Artemia nauplii (<24 h
posthatch) once daily. Salinity, water temperature, dissolved oxygen, and pH
were measured daily in each test jar. Surviving mysids were counted daily.
Aeration was not provided to test solutions until it was observed that
dissolved oxygen concentrations were dropping to near 40% of saturation. Test
temperatures were ambient room temperatures. A lighting cycle was not
established because of the need for overhead lighting during prolonged work
periods. Attempts were made to minimize ambient laboratory light during the
night by covering test containers with aluminum foil.
4.6.2 Indigenous Zooplankton Toxicltv Tests
Copepods were examined with a dissecting microscope and sorted according to
apparent likeness in body form, color, and size. Individuals were not
identified taxonomically, and it is probable that test organisms included more
than one species.
Copepods were held in a 10-L polycarbonate carboy in seawater continuously
stirred with a rotating glass rod powered by a Dayton model 278088 20-rpm
motor. Although feeding activity was not observed, copepods were fed daily
with the unicellular alga, Isochrysis galbana, and brine shrimp nauplii,
Artemia salina. The age of copepods used in the tests was not determined.
Procedures for the indigenous zooplankton toxicity tests were a modification
of those outlined in "Bioassay Procedures for the Ocean Disposal Permit
Program" (EPA, 1978). Copepods were exposed for approximately 48"h in glass
50-mL jars containing 50 ml of the test solution. Five to 10 copepods were
distributed to each test jar at the time of test initiation. Each test
treatment (sample) included six replicate test jars, but only replicates 1,3,
26
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and 5 were used to calculate % survival, providing consistency with the mysid
tests. A seawater control treatment was tested concurrently with the T = 4 h
sludge plume sample.
Test chambers were not aerated. Test jars, however, were placed on an orbital
shaker and gently agitated to minimize dissolved oxygen depletion. Salinity,
water temperature, dissolved oxygen, and pH were measured once daily.
Lighting and room temperature were ambient. Surviving copepods were counted
daily.
4.6.3 Sea Urchin Fertilization Tests
Adult sea urchins, Arbacia punctulaia, were held in a 20-gal aquarium equipped
with a temperature-controlled Ranco chiller and a carbon filtration unit.
Seawater was continuously circulated through the chiller and the carbon
filter. Animals were originally obtained from the Marine Biological
Laboratory (MBL), Woods Hole, Massachusetts. They were separated by sex, and
approximately 20 of each sex were stocked in separate compartments within the
aquarium. A supply of fresh kelp, Laminaria sp., also obtained from MBL, was
distributed to each compartment to provide a continuous supply of food
throughout the duration of the cruise. Salinity, water temperature, dissolved
oxygen, and pH were measured daily, and water exchanges were made daily.
Procedures for the sea urchin fertilization test were based upon those
described in "Short-term Methods for Estimating the Chronic Toxicity of
Effluents and Receiving Waters to Marine and Estuarine Organisms" (EPA, 1988).
Sea urchin sperm and eggs were exposed to test solutions in 20-mL glass
scintillation vials containing 5 mL of test solution. The test design
included four dilutions of sludge sample (12.5%, 25%, 50%, and 100% samples),
and five replicate test vials for each dilution level. Sludge samples
collected at approximately T = 0, 1, 2, 3, and 4 h were tested. A seawater
control treatment was included with each sample tested. In addition, Duxbury
Bay seawater controls and a reference toxicant series (copper sulfate) were
included in each test array.
27
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Sperm were collected with a 1-mL blunt-tipped syringe by stimulating males to
release sperm with the electrodes of a 12-V transformer. Sperm from at least
four males were combined in a scintillation vial and immediately cooled in
ice. The material was then diluted to approximately 7.0 x 106 cells per
milliliter based upon absorbance readings on a Spectronic 21 spectrophotometer
at 540 nm and cell counts on a Neubauer hemacytometer. A 50-/*L aliquot of
diluted sperm was added to the test solution in each test vial. Test vials
were then incubated for 1 h at approximately 20°C.
Eggs were collected with a 5-mL blunt-tipped syringe by stimulating females
with the electrodes. Eggs from at least four females were combined and washed
by gently centrifuging and exchanging seawater. The eggs were then diluted to
a concentration of approximately 2000 cells per milliliter based upon egg cell
counts on a Sedgewick-Rafter cell. One hour after addition of the sperm, a 1-
mL aliquot of the egg suspension was added to each test vial, and the test
array incubated for an additional 20 min. The test was terminated by the
addition of 2 ml of 10% buffered formalin.
Some test vials were analyzed on board to determine the number of fertilized
versus unfertilized eggs. A total of 100 eggs was examined with a compound
microscope at lOOx magnification. Fertilized eggs were defined by the
presence of a fertilization membrane. Test vials that were not analyzed on
board were returned to Battelle for subsequent analysis.
28
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5.0 OCEANOGRAPHIC CONDITIONS
5.1 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 CTD profiling
system described in Section 3. These data were analyzed in several ways to
provide information relevant to the objectives of the survey. These include
. Analyses of temperature/salinity data for identification of shelf water,
slope water, and Gulf Stream warm-core eddies in the vicinity of the 106-
Mile Site
• Comparison 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
5.1.1 Satellite Imagery
Ocean frontal maps were produced from satellite color thermal images that were
obtained from NOAA. The sea-surface temperature and ocean frontal structure
for September 7 are shown in Figure 5-1. The surface expression of the shelf-
slope front advanced onto the continental shelf during this period. In
addition, two warm-core rings, 88-C and 88-E, were moving through the area.
Ring 88-C, centered at about 38°N and 73°W, had apparently spun a tongue of
shelf water into the slope region very near the 106-Mile Site. This shelf
water tongue was colder (19° to 21eC) than the surrounding slope water (23°C).
Ring 88-E, centered at about 39'N and 70'W, was approximately 150 km east of
the Site.
By September 20, the frontal analysis shows significant changes in-the
vicinity of the 106-Mile Site (Figure 5-2). The 106-Mile Site was surrounded
by a relatively homogeneous slope water mass and was not influenced by any
rings. The shelf-slope front had relaxed to near its mean position at the
29
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42N
41N
W&ierWiitMiiiiiS®
Gulf Stream!
36N
75U 74U 73U 72U 71U 70U 6QU
LONGITUDE ('
FIGURE 5-1.
SATELLITE IMAGERY OF OCEAN FRONTAL DATA FOR SEPTEMBER 7, 1988.
THE SURFACE WATER TEMPERATURE IS SHOWN IN DEGREES 'CENTIGRADE.
30
-------
42N
Shelf 117
Water
• ••'. ^^^^•IVII li
75U
74U 73U 72U 71U 70U 60U
LONGITUDE (°W)
FIGURE 5-2.
SATELLITE IMAGERY OF OCEAN FRONTAL DATA FOR SEPTEMBER 20
1988. THE SURFACE WATER TEMPERATURE IS SHOWN IN'DEGREES*
CENTIGRADE.
31
-------
shelf break. Ring 88-C disappeared from the image, being reabsorbed into the
Gulf Stream. The tongue of shelf water also disappeared. A remnant of the
tongue was visible in an image from September 12 (not shown). Ring 88-E moved
west slightly but was still 100 km east of the Site.
5.1.2 Hater Masses
5.1.2.1 Horizontal Gradients
The vertical profile taken at Background Station BG-21 (located about 10 km
north of the Site on September 16) shows a rather typical summer.profile
(Figure 5-3). A shallow mixed layer was observed to a depth of 25 m,
overlaying sharp gradients in temperature, salinity, and density. The mixed-
layer temperature was 23°C with a salinity of 35 °/oo. The surface layer
temperature is consistent with the ocean frontal analysis, indicating the
presence of slope water at BG-21. The turbidity (L) is nearly uniform at
about 10% in the mixed layer. A turbidity maximum is apparent just above the
pycnocline, showing the typically observed accumulation of particles at the
bottom of the mixed layer. The surface layer exhibits higher turbidity than
does the deep layer. This structure of the turbidity profile is consistent
with observations on previous surveys (EPA, 1988b, 1992c).
Using CTD profiles (like that shown in Figure 5-3) from each farfield station,
horizontal contours of the mean mixed-layer salinity, temperature, and
turbidity were calculated. Due to sparse grid spacing, contours of equal
salinity were subjectively drawn over the station array (Figure 5-4). The
contours indicate the presence of a mass of fresher water to the southwest of
the 106-Mile Site, which is consistent with the tongue of shelf water observed
in the September 7 satellite image. These data suggest that the tongue of
shelf water (or a remnant) was still present during the*farfield survey.
It is more difficult to draw conclusive contours of constant mixed-layer
temperature over the station array. However, the data (Figure 5-5) indicate
that warmer water is present at the southern end of the 106-Mile Site near
32
-------
TURBID! TY (%} 0
10
20
30
50
OXYGEN (nl/l) 2
SICMA-T 20
.SALINITY (PPT) 30
TEMPERATURE (C) 5
0
24 25 26 27 28 29 30
fe Temperature
Sa Salinity
Sigma-T Density
DO Dissolved Oxygen D0
Turbidity
60
FIGURE 5-3. VERTICAL PROFILE OF WATER PROPERTIES AT STATION BG-21.
33
-------
39.4
39.2
39.0
ui
5
38.8
38.6
38.4 'r
38.2 <-
Shelf Water
< 330/oo
Slope Water
> 34°/oo
Slope Water
> 34'
-72.5 -72.3 -72.1 -71.9 -71.7 -71.5
LONGITUDE (BW)
FIGURE 5-4.
c °F MIXED-LAYER AVERAGE SALINITY OVER THE FARFIELD
STATIONS. SALINITY VALUES ARE SHOWN (IN °/oo) NEXT TO EACH
STATION SYMBOL. CONTOURS ARE DRAWN AT 0.5 °/oo INTERVALS
34
-------
39.2
39.0
g
§
38.8
38.6
38.4 -
38.2
21.3 \
24-rT
22.0
21.8
21.7
21.4
21.7
22r
o
b22.1
I
'
22.1 22.0
21.5
21
-72.5 -72.3 -72.1 -71.9
Slope Water
Warmer
Slope Water
" Warmer
-71.7 -71.5
LONGITUDE
FIGURE 5-5.
CONTOUR PLOT OF MIXED-LAYER TEMPERATURE OVER THE FARFIELD
STATIONS. TEMPERATURE VALUES ARE SHOWN (IN DEGREES
CENTIGRADE) NEXT TO EACH STATION SYMBOL. CONTOURS ARE DRAWN
AT 0.5°C INTERVALS.
35
-------
Stations FA-3 and FB-3, which is consistent with the mixing of shelf and slope
water masses at the 106-Mile Site.
5.1.2.2 Vertical Gradients
Contours of the vertical profiles of .salinity, temperature, density, and light
transmission along each of the farfield transects are shown in Figures 5-6
through 5-8. These data are consistent with a wedge of colder, fresher, and
less dense water protruding into the 106-Mile Site from the west. Transect A
shows higher turbidity at the southern end of the 106-Mile Site compared to
water outside (particularly north and east) of the Site. The turbidity hot
spots increase with depth toward the south (Figure 5-6), suggesting a downward
movement of a plume (or several plumes). Another feature that is visible in
the B transect (Figure 5-7) is the sharp increase in temperature and salinity
at the southern end of the transect. Note that it does not manifest itself at
the surface, but is clearly present below about 10 m. This is probably the
remnant of Ring 88-C after it rejoined the Gulf Stream.
5.1.3 Hvdroqraphic Conditions at the 106-Mile Site
Analysis of the farfield CTD profiles and satellite thermal imagery result in
the following conclusions about the background hydrographic conditions in the
region of the 106-Mile Site during the September 1988 survey.
• The surface water in the vicinity of the 106-Mile Site was a relatively
homogeneous mass of slope water, with a finger of shelf water protrudina
into the southern half of the Site. However, the subsurface water (down
to the pycnocline) was a confusing mixture of different water masses.
• There were large horizontal salinity variations in the upper 50 m of the
water column owing to the influx of both highly saline water (Gulf
Stream) from the periphery of warm-core Ring 88-C and fresher shelf water
in the form of a surface layer tongue.
• The seasonal pycnocline was situated between roughly 20 and 45 m and
coincided with the sharp pycnocline maintained by the interface between
the surface layer of shelf water and the underlying slope water in the
presence of the shelf-water tongue. '
36
-------
TEMPERATURE CO
38°50'N
TRANSECT A
FIGURE 5-6.
VERTICAL PROFILE OF WATER PROPERTIES FROM FARFIELD TRANSECT A
(REFER TO FIGURE 3-1 FOR TRANSECT LOCATIONS).
37
-------
TEMPERATURE CO
345
SALINITY CPPT)
3 4 5
SO
38°50'N
TURBIDITY (X)
345
50
3B°20'N
30
38°50'N
TRANSECT B
30
38°20'N
FIGURE 5-7. VERTICAL PROFILE OF WATER PROPERTIES FROM FARFIELD TRANSFPT R
(REFER TO FIGURE 3-1 FOR TRANSECT LOCATIONS).
38
-------
TEMPERATURE (C)
4 3
50
39°15'N
SALINITY
4 3
so
38°50'N
30
39°15'N
TRANSECT C
FIGURE 5-8.
TRANSECT c-
39
-------
At depths greater than 50 m, water properties were representative of
slope-water conditions.
A subsurface expression of the Gulf Stream was within 15 km of the
southern boundary of the 106-Mile Site.
5.2 NEAR-SURFACE CURRENTS
Near-surface currents were determined from Lagrangian drifter tracks by using
both visually tracked and satellite-tracked drogues. Data from "the expendable
current profilers are not available due to equipment malfunction.
5.2.1 Near-Surface Drifter Results
.5.2.1.1 Visually Tracked Drogues
The trajectories of the visually tracked mixed-layer drogues deployed during
the nearfield phase of the survey are shown in Figure 5-9. A summary of the
drogue behavior is given in Table 5-1. The drogues deployed in plume tracks
DB-21 and DB-22 move southwest at an average speed of 12 cm/s. The DB-23
drogue, on the other hand, moved southeast at an average speed of 22 cm/s.
The general southerly movement of the drogues (and the near-surface water
mass) is consistent with previous observations and the satellite imagery data.
The spatial and temporal resolution of the satellite 'imagery and CTD profiles
were not sufficient to determine the exact location of the shelf-slope front.
However, the data for the DB-23 drogue indicate that it was deployed in shelf
water, and its movement to the southeast was driven by the clockwise movement
of Ring 88-C.
These measurements indicate that the surface layer was migrating weakly to the
southwest, but the intrusion of the tongue of shelf water introduced a
horizontal shear, driving a portion of the surface water more rapidly to the
southeast.
40
-------
39 2'N
38 SB'N
3B 54'N
3B 50'N
DB21
SHALLOW DROGUE
END
OB22
SHALLOW
DROGUE
DB21
SHALLOW DROGUE i
BEGIN
106-MILE SITE
DB23.
SHALLOW
DROGUE
72 8' W
72 4* W
72 0' W
71 56' W
FIGURE 5-9.
TRAJECTORIES OF THE VISUALLY TRACKED MIXED-LAYER DROGUES
DEPLOYED DURING THE PLUME TRACKING OPERATIONS.
41
-------
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O a,
•i- S;
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CM ~H
vo r->
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42
-------
5.2.1.2 Satellite-Tracked ARGOS Drifters
The satellite-tracked shallow drogue trajectories in the immediate vicinity of
the 106-Mile Site are shown in Figure 5-lfl. Tick marks along the tracks
indicate the daily noontime position. All of the drifters eventually moved to
the southwest and remained in the slope water during the entire survey.
Drifter No. 7265, released on September 18, moved eastward and then north of
the 106-Mile Site and finally to the southwest. The speed of the drifters is
apparent in the daily tick-mark locations. While the September 17 and 18
drifters moved rapidly out of the area, covering as much as 40 km in a day,
the September 16 drifter stalled for about a week after moving west away from
the 106-Mile Site. Eventually, however, it continued on its way to the
southwest.
The satellite-tracked deep (50 m) drogue drifter trajectory is shown in Figure
5-11. This drifter was carried immediately and rapidly out of the Site and
toward the southeast. The CTD and turbidity profiles indicated that the north
wall of the Gulf Stream extended below the mixed layer into the southeastern
edge of the farfield station array. Thus, the deep-water drifter was probably
entrained directly into the Gulf Stream.
Long-term movement for all four satellite-tracked drifters is shown in Figure
5-12. Information on the deployment and last known position of the drifters
is summarized in Table 5-2. As seen in Figure 5-12, all of the shallow
drifters eventually were carried southwest and became entrained in the Gulf
Stream. Once in the Gulf Stream, they moved quickly out into the north
Atlantic. The 50-m drifter was carried from the Site directly into the Gulf
Stream and then east as far as 42°W before its batteries were depleted.
43
-------
43N-
200 m
AON-
200 m'
fc-S'
I
73W
AON-
39N"
10-m drogue (#7266)
released 9/16/88
106-Mile Site
72W
200 m
5^ drogue (#7265)
reteased 9/18/88
10-m drogue (#7264)
released 9/17/88
39N f
3BN'
73W
72W
3BN-
73W
72W
71K
FIGURE 5-10.
SHORT-TERM TRAJECTORIES OF THE SATELLITE-TRACKED MIXED-LAYER
DROGUES DEPLOYED DURING THE PLUME-TRACKING OPERATIONS. TICK
MARKS INDICATE THE DAILY 12:00 N POSITIONS.
44
-------
4 ON
3SN
38N
73W
ZOO
/
50
-------
42 H
i N
40 N
39 N -
38 N
37'N
36 N -?
35'N
5-m drogue (#7265)
released 9/18/88^
10-m drogue (#7266)
released 9/16/88
72 W
70 W
68 H
66 W
64 W
.42 N
41 -H -
10-m drogue (#7264)
released 0/17/88
50-rn drogue (#7267)
released 8/11/88
37 'N
36 N
35 N
76
70 W
68 W
E6 W
64 H
FIGURE 5-12.
LONG-TERM TRAJECTORIES OF THE SATELLITE-TRACKED DROGUES
DEPLOYED DURING THE PLUME-TRACKING OPERATIONS. SHORT-TERM
TRAJECTORIES ARE SHOWN IN FIGURES 5-10 AND 5-11.
4b
-------
6.0 NEARFIELD FATE OF SEWAGE SLUDGE
'The EPA conducted two previous surveys to monitor the nearfield fate of sewage
sludge dumped at the 106-Mile Site under'summer ( EPA , 1992c) and winter
( EPA , 1988b) conditions. The results from these two surveys and
preliminary results from the September 1988 survey were discussed in detail in
the document "Determination of Sludge Dumping Rates for the 106-Mile Site"
( EPA 1992d). Results from the September 1988 survey are summarized
below.
6.1 BARGE RECORDS AND DUMPING RATES
The Ocean Dumping Notification Forms submitted to EPA following each dumping
event provide information on 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 important to characterize sludge plume
behavior because the initial size of the plume, the concentration of sludge
within the plume, and the rate of initial mixing all depend upon the dumping
characteristics of the barge. Dumping information for the barges studied
during the September 1988 survey is summarized in Table 6-1. All three barges
contained similar volumes of sludge and dumped at approximately the same rates
(12,000 to .14,000 gal/min).
Of more importance in the analysis of plume behavior are the actual sludge
dumping rates and 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 foot of track length (i.e., the effective dumping rate) can be
obtained by dividing the volume of sludge by the total length of the plume.
The effective sludge dumping rates are listed in Table 6-1 as function of both
time and distance.
47
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TABLE 6-1. SUMMARY OF DUMPING INFORMATION FOR PLUME STUDIES CONDUCTED DURING
SEPTEMBER 1988 SURVEY AT THE 106-MILE SITE3
Survey
Date
Tug
Barge
Sludge volume (gal)
Disposal time (h)
Disposal length (nnri)
Barge speed (kn)
Average dump rate (gal /mi n)
(gal/ft)
DB21
09-16
Kate
Princess B
3,125,000
4.3
20
4.65
12,110
30
DB22
09-17
Heide Moron
Spring Creek
3,403,400
4
25
6.25
14,180
26
DB23
09-18
Alice Moron
Lemon Creek
3,516,000
4.1
27
6.6
14,290
25
Data are from Dumping Notification Forms.
48
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6.2 ESTIMATES OF PLUME WIDTH AND HORIZONTAL HIXIXNG
Physical oceanographic and transmissometry (turbidity) data were collected in
the nearfield during plume-tracking events to monitor the horizontal structure
of the upper water column during plume-tracking operations and to monitor
plume behavior with measurements of turbidity. Water column physical
parameters were measured with the BOSS and currents were inferred from drifter
motions. The survey vessel crisscrossed the plumes, towing the BOSS at
constant depth below the surface. The location of the horizontal profiling
activities during plume tracking within and near the 106-Mile Site is shown in
Figure 6-1. Additional information on tow depth and duration is given in
Appendix B.
Light transmission data from a 4-m-deep horizontal profile taken during the
DB-23 plume track (Figure 6-2) are typical of the transmissometer profiles
observed during plume crosstows. Beam attenuation (turbidity) increases from
the background level of about 10% to as much as 50% to 60% as the BOSS
traverses the plume and then returns to background level upon exiting the
plume.
Plume-width data were evaluated for plume events DB-21 and DB-23. Estimates
of plume width were determined from horizontal, profiles of turbidity by using
the shipboard profiling system with the CTD/transmis"someter. These analyses
were conducted in the same manner as the analyses of plume width from the
September 1987 survey data (EPA , 1992c).
The plume width for DB-23 increased from roughly 250 to 400 m during the 6 h
following disposal (Figure 6-3). Both the magnitude and rate of change of
plume width for DB-23 were similar to the observations during September 1987
and March 1988 (Figure 6-4).
In general, the observed plume widths for DB-21 and DB-23 during the first
hour after disposal were similar to the results of the two previous 106-Mile
Site surveys conducted in September 1987 and March 1988 (Figure 6-4). Plume-
width data shown in Figure 6-4 were obtained from horizontal profiling for
49
-------
39 15'N
39 10'N
3S-22
39 S'N
£
w
39* O'N
3B*S5'N
3B*SO'N
72*10* H
3Q-21
106-HILE SITE
QB-22
j 08-21
I
72' 5' H 72* 0* H
LONGITUDE ("W)
71'55' W
FIGURE 6-1.
LOCATION OF HORIZONTAL PROFILES TAKEN DURING BACKGROUND
SAMPLING AND PLUME TRACKING.
50
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ts
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five plumes (DB-2, DB-4, DB-10, DB-21, and DB-23) and from aerial photography
( EPA 1992c) for four plumes (DB-1, DB-2, DB-3, and DB-10). The magnitude
and rate of change of plume width during the first hour are similar for the
three surveys. All show a sharp increase-in plume width during the first 15
min, then a more gradual increase. Except for DB-4, all plume widths measured
from 150 to 250 m after 1 h. • ..
The results of the various aerial and horizontal profiling analyses of plume
width are summarized below.
• Plume widths and rate of horizontal spreading were similar during the
three surveys (two conducted in summer and one in winter). Wind and wave
conditions also were similar.
• Horizontal spreading rates were greatest during the first 10 to 15 min
after dumping owing to turbulent mixing in the wake of the barge.
6.3 SLUDGE DILUTION RATES
Calculations of sludge dilution are necessary to determine that limiting
permissible concentrations (LPC) are not exceeded at the site 4 h after sludge
disposal, to estimate concentrations of water quality criteria (WQC)
contaminants when those contaminants cannot be measured directly in sludge
plumes, and to develop and verify dumping rate models ( EPA , 1992d). Data
for TSS and, total metals in the source sludge and receiving waters were used
to calculate sludge dilution for plumes monitored during this survey. These
results are discussed below. Estimates of dilution for the entire plume using
plume volume and transmissometry data were not performed because of the
uncertainties associated with those calculations ( EPA , 1988b, 1992d).
6.3.1 Sludge Characterization Results
The plumes of three barges were sampled during this survey: Princess B (Plume
DB-21), Spring Creek (Plume DB-22), and Lemon Creek (DB-23). Samples of
source sludge from these barges, and from the barge Udalls Cove were analyzed
for the metals Cd, Cu, Fe, Pb, Hg, and Zn; and for specific gravity, total
54
-------
residue, and nonfilterable residue (Table 6-2). These data are used below ;to
estimate sludge dilutions.
6.3.2 Sludge Dilution Based on TSS Data
The changes in TSS concentration for plumes DB-21, DB-22, and DB-23 following
dumping are presented in Figure 6-5. The initial TSS values were much higher
for DB-21 than for the other plumes, and the TSS never reached background
levels (0.16 to 0.55 mg/L) during the 9-h sampling period. Plume DB-22
reached background levels of TSS within 3 h of initial disposal,.whereas
DB-23 required greater than 8 h (based on extrapolation of plot).
Dilution was estimated by dividing the measured TSS concentrations in the
source sludge (Table 6-2) by the mean plume-TSS concentration (listed in
Tables C-l through C-3I; Appendix C)~. The TSS concentrations in sludge plumes
at T = 0 h ranged from 2.9 to 15 mg/L, corresponding to initial sludge
dilutions ranging from 880:1 to 1900:1 (Table 6-3). These initial sludge
dilutions are similar to those determined in the summer 1987 survey where
literature values were used for TSS in the source sludge ( EPA , 1992c).
The rates of sludge dilution are shown graphically in Figure 6-6. As noted
above, the intial dilutions for all three plumes were similar. However, plume
DB-22 exhibits a dramatic increase in the rate of dilution after 2 h,
indicating that a more active mixing process might have occurred. Dilution
values for DB-21 and DB-23 after 8 h were both about 3000. These are low
dilutions relative to DB-22 and previous estimates (EPA, 198.8b, 1992c) . The
variability of the TSS data in this survey was much lower than that found in
the Winter 1988 survey ( EPA 1988b). Thus, these data provide a more
precise estimate of sludge dilution than did the data from the previous
survey.
55
-------
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56
-------
TABLE 6-3. INITIAL DILUTION ESTIMATES OBTAINED DURING THE SEPTEMBER 1988
106-MILE SITE SURVEY. INITIAL DILUTIONS ARE CALCULATED FROM
CONCENTRATIONS IN THE SLUDGE PLUME AT TQ AND IN SOURCE SLUDGE.
PLUME
DB21
DB22
DB23
INITIAL DILUTION
Cu
1700
5400
7900
Pb
970
5000
6000
Cd
1200
1800
1400b
Fe
1100
7000
10,000
Zn
1200
2800
6600
Mean±(SD)a
1200±(280)
4400±(2080)
7600±(1770)
TSS
1000
1900
880
^Standard deviation (SD).
DData not used in calculation of mean.
57
-------
on
tn
DB21
15
4 6
TIME AFTER DISPOSAL, h
10
10 —
en
E
tn
tn
DB22
15
4 6
TIME AFTER DISPOSAL, h
10
,10-4-
cn
tn
tn
5-1-
DB23
4 6
TIME AFTER DISPOSAL, h
10
FIGURE 6-5.
CONCENTRATION OF TSS IN THE PLUME VERSUS TIME FOR PLUMES
DB-21, DB-22, AND DB-23.
58
-------
o
o
o
o
o
c
o
o
o
o
4000
3000 --
2000-•
1000
8E4
6E4--
4E4--
2E4--
0
•5000 -T-
4000 - -
3000 - -
2000 - •
toooi
0
4 6
TIME AFTER DISPOSAL, h
8
2. 3
TIME AFTER DISPOSAL, h
10
DB22
DB23
TIME AFTER DISPOSAL, h
FIGURE 6-6. SLUDGE DILUTION RATES BASED ON MEASURED TSS CONCENTRATIONS,
59
-------
6.3.3 Sludge Dilution Based on Total Metal Data
Cadmium, copper, iron, lead, nickel, and zinc were selected as chemical
tracers of sludge based on their relatively high concentrations in sludge
dumped at the site (Table 6-2), their ease of analysis, and their successful
use as tracers during previous surveys (EPA, 1988b, 1992c). The total metal
concentrations in the three plumes are listed in Tables C-l through C-3 and
plotted as a function of time in Figures C-l through C-5, Appendix C. Sludge
dilution values based on total metal data are listed in Tables C-4 through C-
9, Appendix C. A summary of these data is given below.
The initial sludge dilution for each plume was estimated from metal
concentrations in the sludge plume at time T = 0 and are listed in Table 6-3.
The initial dilution factors for each barge vary for the five metals that were
measured. Coefficients of variation about the mean range between 20% and 50%.
There is a factor of 6 difference between the mean initial dilutions among the
three barges, with initial dilution increasing in order from DB21, DB22, and
DB23. This range in initial dilution is consistent with dilution estimates
made on previous surveys and is discussed in detail in the document
"Determination of Sludge Dumping Rates for the 106-Mile Site" ( EPA
1992d).
Estimates of sludge plume dilutions over time were determined from the metal
concentration data up to the first 9 h following a dumping event. These data
are listed in Appendix C and are shown graphically as dilution curves in
Figure 6-7. The plumes from DB-21 and DB-23 exhibit similar rates of dilution
that are characteristic of weak mixing, although DB-23 had a greater initial
dilution (Table 6-3). A significantly higher rate of dilution was observed
for plume DB-22, even though its initial dilution was less than that of DB-
23. The higher overall rate of dilution for DB-22 could be due to more active
mixing conditions after disposal ( EPA , 1992d) or the sludge type
contained in the Spring Creek (DB-22).
60
-------
o
D
O
O •!— O Cadmium
• Cepp«r
A A Iron
A A Lead
D DZInc
4 6
TIME AFTER DISPOSAL, h
250,000
200,000
i_ .
g 150,000--
u_
c
'I 100,000
25
50,000--
O —— O Cadmium
• — • Copp«r
A A Iron
A AUod
D O Zinc
DB22
2 3
TIME AFTER DISPOSAL, h
12000
£
o
£
c
9000 - -
6000 --
3000 -•
DB23
O — O Cadmium
• • Copper
A — & Iron
A AL«ad
D DZinq
TIME AFTER DISPOSAL, h
FIGURE 6-7. SLUDGE PLUME DILUTION CURVES BASED ON MEASURED TOTAL METAL
CONCENTRATIONS.
61
-------
The form of the dilution curves and the relative dilution rates based on
metals data (Figure 6-7) are similar to those observed for the TSS data
(Figure 6-6), but the actual dilution values calculated for TSS are lower than
those calculated for metals.
To determine which, if any, parameter was significantly more useful as a
tracer of sewage sludge, metal concentrations from individual samples were
plotted one against another to determine how well the results for one metal
predicted the behavior of the other tracer metals. Metal concentrations were
plotted against those of iron, the metal with the highest concentration in the
sludge (Figures 6-8 and 6-9). A strong correlation (r > 0.90) was found
between iron and all metals for plumes DB-21 and DB-22, except for Ni in plume
DB-22 (r = 0.41). In plume DB-23, a strong correlation was found between Fe
and Cu, Pb, and Zn; a weaker correlation (r < 0.65) was found with Ni and Cd.
Only plume DB-22 exhibited a strong correlation (r = 0.98) between Fe and TSS.
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 sludge load. This consistent
metal behavior was observed on a previous survey ( EPA , 1988b).
Figures 6-8 and 6-9 also illustrate that metal ratios may be used to develop
sludge 'isignatures" that can be used to trace and identify individual sludge
plumes throughout the nearfield. 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.
62
-------
en
U
"5
^^
o
20
0.500
-o
o
J3
0.
3
O
40 60
Total Fe. /*g/L
80
20
100
O DB21
A DB22
D DB23
100
Total Fe, fig/L
FIGURE 6-8.
PLOTS OF TOTAL CU, CD, AND PB VERSUS TOTAL FE IN SAMPLES
COLLECTED FROM PLUMES DB-21, DB-22, AND DB-23.
63
-------
A DB22
504- D DB23
40 60
Total Fe,
100
1.500
z
1.000--
0.500 -
0.000
O DB21
A DB22
O DB23
20
40 60
Total Fe. pg/L
80
100
20
15
in 10 +
tn
5-
O DB21
A DB22
D DB23
-a o
20
40 60
Total Fe. /xg/L
80
100
FIGURE 6-9.
PLOTS OF TOTAL ZN, NI, AND TSS VERSUS TOTAL FE IN SAMPLES
COLLECTED FROM PLUMES DB-21, DB-22, AND DB-23.
64
-------
6.4 WATER QUALITY MEASUREMENTS
Ammonia and pH were measured in water samples collected during the plume
tracking to monitor any changes in these..common water quality parameters. The
values of ammonia and pH measured at the background stations and within the
plumes are listed in Appendix C, Table C-13. These data are plotted as a
function of time in Figures 6-10 through 6-12 for DB-21, DB-22, and DB-23,
respectively.
At the background stations north of the dump site, the pH ranged from 8.11 to
8.24. The pH ranged from 7.95 to 8.17 in plume DB-21, from 8.21..to 8.38 in
plume DB-22, and from 8.22 to 8.30 in plume DB-23. The only suggestion of a
decrease is in plume DB-21; the pH in this plume is about 0.1 to 0.2 pH units
lower than the pH observed at the reference station and in the other plumes.
This might be due to the more acidic sludge dumped in plume DB-21. For the
dumping event DB-21, the pH of the sludge ranges from 4.3 to 4.6, whereas the
pH of the sludge from events DB-22 and DB-23 is 5.4 to 7.0. Overall, the pH
data indicate that sludge dumping has no impact on the pH of the receiving
waters at the 106-Mile Site. This is not suprising considering the rapid
dilution of the sludge and the extremely high pH buffer capacity of the ocean
(Stumm and Morgan, 1981).
The concentration of ammonia measured at the background stations and within
the plumes ranged from O.01 to 0.31 mg/L. The detection limits ranged from
0.01 to 0.1 mg/L, depending on instrument stability. Thus, most ammonia
concentrations were at or near the detection limit and the small differences
are not significant. Ammonia concentrations ranged from <0.1 to 0.22 mg/L at
the background stations, from <0.1 to 0.31 mg/L in plume DB-21, from 0.04 to
0.18 mg/L in DB-22, and from <0.01 to 0.25 mg/L in DB-23.
65
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6.5 COMPARISON OF RESULTS AGAINST HATER QUALITY CRITERIA (WOO
Results of analysis of samples collected within the plumes indicate that water
quality criteria (EPA, 1986) were met for-most of the parameters measured.
All of the pH values were within the range specified (6.5 to 8.5) for chronic
marine criteria. Comparison of the metal data against marine WQC is shown in
Figure 6-13 for Cu and Figures C-l through C-5 (Appendix C) for the other
metals. Concentrations of Cd, Ni, and Zn were below chronic marine WQC (9.3,
8.3, and 86 /jg/L, respectively) in all samples. Concentrations of Pb were
below the marine acute WQC (140 pg/L) in all samples, but exceeded the chronic
marine WQC (5.6 ftg/l) 4 h after disposal for plume DB-21 and 7 h after
disposal for plume DB-23. The samples for DB-23 were collected outside the
boundary of the 106-Mile Site. Concentrations of Cu exceeded the marine WQC
(2.9 /ig/L for both acute and chronic) in the initial samples for all plumes
and 4 h after disposal for plumes DB-21 and DB-23. These results are in
agreement with the previous summer survey to the 106-Mile Site ( EPA
1992c), where WQC were exceeded for Cu and Pb only.
69
-------
15 -r-
104-
8
DB21
15
10
*
15
I
4 6 ,
TIME AFTER DISPOSAL, h
4 6
TIME AFTER DISPOSAL, h
10
DB22
10
DB23
5 4-
4 6
TIME AFTER DISPOSAL, h
10
FIGURE 6-13.
PLOTS OF COPPER CONCENTRATIONS IN THE SLUDGE PLUME VERSUS TIMF
FOR PLUMES DB-21, DB-22, AND DB-23. MARINE WATER QUALITY
CRITERIA FOR COPPER ARE ACUTE: 2.9 n/L; CHRONIC: 2 9"J/L.
70
-------
7.0 BIOLOGICAL EFFECTS
To assess the potential for biological impacts within the 106-Mile Site, the
following activities were completed:
• Measurement of chlorophyll a and phaeophytin concentrations to
assess the impact of sludge on primary productivity
• Performance of on-board toxicity tests of sludge plume samples with mysid
shrimp, indigenous zooplankton, and sea urchin gametes
• Collection of fish eggs with a neuston net for examination of genetic
mutations or other developmental abnormalities
• Observations of marine endangered species
• Collection and identification of floatable plastic debris.
7.1 CHLOROPHYLL RESULTS
Chlorophyll a was measured as an estimate of phytoplankton biomass and,
therefore, an indication of primary productivity. Actual incubation
experiments to measure primary production were not performed. Chlorophyll a
concentrations from the plume studies are listed in Table C-12 (Appendix C).
Chlorophyll a concentrations in the water above the pycnocline ranged from
0.17 to 0.46 ftg/L at the background stations and from 0.17 to 0.63 /*g/L within
the sludge plumes. This range is similar to that observed in surface waters
near the 106-Mile Site during the baseline survey ( EPA , 1987). The
concentrations do not vary considerably within or between plumes or between
the sludge plumes and background stations.
Phaeophytin is the primary product of chlorophyll degradation, which occurs
through phytoplankton death and decomposition. In addition, the fluorescence
method used to measure phaeophytin has poor selectivity and sludge components
may contribute to the phaeophytin signal. These complexities could make it
difficult to use these data to assess changes in primary production that
result from the discharge of sludge. If one assumes that the sludge does not
contribute significantly to the analytical signal and that zooplankton grazing
remains constant throughout the survey, then decreases in the chlorophyll a I
71
-------
phaeophytin (C/P) ratio would indicate possible adverse effects on the
phytoplankton community.
Phaeophytin concentrations from the plume studies are listed in Table C-12
(Appendix C). The concentration of phaeophytin in the surface waters was much
lower at the background stations than within the plumes. The background
stations contained 0.10 to 0.23 pg/L phaeophytin. Plumes DB-21 and DB-22
contained similar concentrations of phaeophytin with ranges of 0.32 to 0.87
pg/L and 0.21 to 0.84 pg/L, respectively. Plume DB-23 exhibited higher
phaeophytin concentrations with a range of 0.52 to 1.53 pg/L. The C/P ratios
which are listed in Table C-12 (Appendix C), indicate that only p.lume DB-23
exhibited a significant decrease from background C/P, with about a fourfold
reduction in C/P. The fact that the decreased C/P ratio was due entirely to
an increase in the phaeophytin signal (i.e., there was no decrease in
chlorophyll a) indicates that sludge interference is likely.
7.2 TOXICITY STUDIES
A summary of the samples collected and tests performed for the toxicity
studies was presented above in Table 3-2. Mysid and zooplankton tests were
completed on background samples BG-21 and BG-22 and the T = 4 h sample of the
three sludge plume samples. Sea urchin fertilization tests were completed on
each of the samples collected. All water samples were frozen following use in
the toxicity tests.
7.2.1 Results of Mysid Toxiclty Tests
On September 17 at 0130 h, tests were initiated on sludge sample DB-21 and
background sample BG-21. The test results (Table 7-1) were inconclusive
because of excessive mortality throughout the test array. The poor survival
might have been the result of depressed dissolved oxygen concentrations,
although all measurements were above 40% saturation, the level recommended in
EPA testing guidelines for initiating aeration. Aeration was supplied to each
test chamber beginning at approximately 48 h, when it was observed that
72
-------
TABLE 7-1. RESULTS OF MYSID TESTS FOR SAMPLES BG-21 AND DB-21 (4 h).
Parameter .
Measured3
Dissolved 02 (mg/L)
Salinity(°/00)
Temperature (°C)
PH
Approximate
Observation Time
(h)
24
48
72
96
SW
Control0
5.7±0.92
33.8±0.54
22.1±0.57
7.81±0.18
Water Quality
BG-21
5.6±1.15
33.9±0.20
22.1±0.57
7.80±0.19
Analyses
DB-21. 4 h
5.3±1.30
33.4±0.80
22.1±0.57
7.74±0.20
Percent Survival of Mvsids0
SW -
Control5
100
57
50
50
BG-21
100
70
70
70
DB-21. 4 h
90
80
80
77
Parameters were measured daily in each test chamber, n = 15 measurements for
each parameter. Mean ± standard deviation are reported.
bSeawater control sample collected at 38°51.2'N, 72°27.0'W, on September 16.
cPercent survival: 100 x (number surviving divided by number of mysids at time
of test initiation).
73
-------
significant mortality had already occurred. Mortalities were minimal
following aeration.
The results of tests initiated on samples-DB-22 and BG-22 beginning at 0030 h
on September 18 are shown in Table 7-2. Aeration was added to all test
chambers after the 24-h observation period to prevent dissolved oxygen
concentrations from dropping below 5.0 mg/L. Survival of mysids was > 90%;
the DB-22 and B6-22 samples were considered nontoxic.
The results of tests initiated on sludge sample DB-23 on September 19 at 0400
are shown in Table 7-3. Survival of mysids was > 90% in this sample and the
DB-23 sample was considered nontoxic.
7.2.2 Results of ZoopTankton Toxicitv Tests
The results (Table 7-4) of acute toxicity tests of sample BG-21 and DB-21 with
indigenous calanoid copepods, initiated on September 17 at 0105 h, were
inconclusive because of excessive mortality observed throughout the test
array. Acute toxicity tests on samples from sludge plumes DB-22 and B6-22
(indigenous pontellid copepods) also were inconclusive because of excessive
mortality observed throughout the test array (Table 7-5).
The resujts of acute toxicity tests of samples from s-ludge plume DB-23 on
indigenous calanoid copepods are shown in Table 7-6. The tests were initiated
on September 19 at 1345 h. Survival in the controls was 82%, whereas survival
in sample DB-23 was 80%, indicating that there was no significant toxicity
associated with plume DB-23.
7.2.3 Results of Chronic Toxicitv Tests with Sea Urchins
A summary of test results for the DB-21 sample dilution series is shown in
Table 7-7 and is graphically displayed in Figure 7-1. Dilutions are
represented by the percentage of the original sample concentration by volume
(i.e., percent full strength). At T = 0 h, about 27% of the eggs were
fertilized at 12% and 25% sample concentration. At 50% sample concentration,
74
-------
TABLE 7-2. RESULTS OF MYSID TEST FOR SAMPLES BG-22 AND DB-22 (3.5 h).
Parameter
Measured3
Dissolved 02 (mg/L)
Salinity(°/00)
Temperature (°C)
PH
Approximate
Observation Time
(h)
24
48
72
96
Water Quality Analyses
SW
Control"
6.27±0.66
32.5±0.63
21.4±0.49
7.94±0.17
SW
Control5
100
97
97
97
B6-22
6.11±0.71
.. 33.7±0.70
21.9±0.34
7.95±0.21
Percent Survival
BG-22
100
97
93
93
DB-22, 3.5 h
6.2±0.64
32.8±0.85
21.7±0.47
7.94±Q.19
of Mysidsc
DB-22. 3.5 h
100
100
100
100
Parameters were measured daily in each test chamber, n = 15 measurements for
each parameter. Mean ± standard deviation are reported.
bSeawater control sample collected at 38°51.2'N, 72°27.0'W, on September 16.
cPercent survival: 100 x (number surviving divided by number of mysids at time
of test initiation).
75
-------
TABLE 7-3. RESULTS OF MYSID TESTS FOR SAMPLE DB-23 (4 h).
Parameter
Measured3
Dissolved 02 (mg/L)
Salinity(°/00)
Temperature (°C)
PH
Approximate
Observation Time
24
48
72
96
Water Quality Analyses
SW h "
Control0 DB-23, 4 h
6.3±0.60 6.3±0.55
32.2±0.81 32.9±1.02
21.7±0.42 21.9±0.31
7.88±0.17 7.99±0.15
Percent Survival of Mysidsc
SW
Control0 DB-23, 4 h
100 93
100 93
100 93
100 90
Parameters were measured daily in each test chamber, n = 15 measurements for
each parameter. Mean ± standard deviation are reported.
bSeawater control sample collected at 38°51.2'N, 72°27.0'W, on September 16.
cPercent survival: 100 x (number surviving divided by number of mysids at time
of test initiation).
76
-------
TABLE 7-4. RESULTS OF ZOOPLANKTON TESTS FOR SAMPLES BG-21 AND DB-21 (4 h)
Parameter
Measured* .
Dissolved 02 (mg/L)
Salinity(°/00)
Temperature (°C)
pH
Approximate
Observation Time
(h)
24
48
Water Quality Analyses
SW
Control
6.3±0.
33.3±0.
22.0±0.
7.9±0.
SW
Control
55
32
b B6-21
44 6.5±0.27
94 34±0.0
0 22.0±0.0
14 7.96±0.08
Percent Survival of
b BG-21
40
7
DB-21, 4 h
6.2±0.47
33.3±0.94
22.0±0.0
7.88±0.09
Zooplankton0
DB-21, 4 h
50
10
Parameters were measured daily in three of six test chambers, n = 9
measurements for each parameter. Mean ± standard deviation are reported.
bSeawater control sample collected at 38°51.2'Nf 72°27.0'W, on September 16.
f*
^Percent survival: 100 x (number of surviving copepods divided by number at
time of test initiation).
77
-------
TABLE 7-5. RESULTS OF ZOOPLANKTON TESTS FOR SAMPLES B6-22 AND DB-22 (3.5 h),
Parameter
Measured3
Dissolved 02 (mg/L)
Salinity(°/00)
Temperature (°C)
PH
Approximate
Observation Time
00
24
48
Water
SH
Control0
5.3±0.79
32.0±0.00
23. Oil. 41
7.78±0.23
Percent
sw
Control0
65
26
Quality
BG-22
5.2±0.
34.7±0.
22.9±1.
7.85±0.
Survival
BG-22
67
37
Analyses
DB-22, 3.5 h
89 5.3±0.97
94 34.0±0.00
34 22.9±1.34
24 7.84±0..24
of Zooplankton0
DB-22, 3.5 h
75
50
Parameters were measured daily in three of six test chambers, n = 9
measurements for each parameter. Mean ± standard deviation are reported.
DSeawater control sample collected at 38°51.2'N, 72°27.0'W( on September 16.
^Percent survival: 100 x (number of surviving copepods divided by number at
time of test initiation).
78
-------
TABLE 7-6. RESULTS OF ZOOPLANKTON TESTS FOR SAMPLE DB-23 (4 h).
Parameter
Measured3
Dissolved 02 (mg/L)
Salinity(°/00)
Temperature (°C)
pH
Approximate
Observation Time
(h)
24
48 '
SW .
Control0
6.4±0.72
34.2±0.63
23.2±0.24
7.9±0.19
Percent
SW
Control
92
82
Water Quality Analyses
DB-23, 4 h
6.2±0.85
35.1±0.44
23.4±0.31
7.87±0.21
Survival of Zooplankton0
DB-23. 4 h
90
80
Parameters were measured daily in three test chambers, n = 9 measurements for
each parameter. Mean ± standard deviation are reported.
bSeawater control sample collected at 38°51.2'N, 72027.0'Wf on September 16.
cPercent survival: 100 x (number of surviving copepods divided by number at
time of test initiation) x 100.
79
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TABLE 7-7. RESULTS OF SEA URCHIN FERTILIZATION TESTS COMPLETED FOR THE
DB-21 SAMPLE SERIES AND BACKGROUND SAMPLES B6-21 AND B6-22.
Sample
DB-21, 0 h
Duxbury Bay SW Control
SW 6-1, SW Control
DB-21
DB-21
DB-21
DB-21
DB-21, 1 h
SW 6-2, SW Control
DB-21
DB-21
DB-21
DB-21
DB-21, 3 h
Duxbury Bay SW Control
SW 6-6 SW Control
DB-21
DB-21
DB-21
DB-21
DB-21, 4 h
SW 6-7 'SW Control
DB-21
DB-21
DB-21
DB-21
Background Samples
BG-21, background
BG-22, background
Dilution
(% Sample)
NAa
.. NA
12
25
50
100
NA
12
25
50
100
NA
NA
12
25
50
100
NA
12
25
50
100
NA
NA
Egg
Fertilization
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only 17% of the eggs were fertilized; at 100% sample concentration, 12% of the
eggs were fertilized. In the T = 1 h sample, fertilization was greatly
reduced to 3% and 4% at the 12% and 100% sample concentrations, respectively.
At T = 3, fertilization at all dilutions^except 100% sample concentration was
very good; at T = 4, there was little toxic effect at any dilution.
7.3 FISH EGG ABNORMALITIES
The results of observations on chromosomal abnormalities in developing fish
embryos collected at the 106-Mile Site are summarized in Table 7-8. There
were relatively few eggs in any of the samples, probably because of the time
of year that the samples were collected. Most of the eggs that were collected
did not appear to show any embryonic development, but they may have been
unfertilized. Many of the squashes contained a great deal of necrotic
material. Those embryos observed were mostly in the late gastrula stage of
development. All mitotic figures observed in the squashes were normal.
Photomicrographs of the mitotic figures are archived at Battelle.
7.4 ENDANGERED SPECIES
A qualified observer from the Manomet Bird Observatory performed the cetacean
and marine turtle population assessment. The observer collected data on the
distribution and abundance of seabirds at the study site. No unusual
observations (or lack of sightings) were recorded. The full report submitted
by the Manomet Bird Observatory is given in Appendix D.
7.5 FLOATABLE DEBRIS
The zooplankton and fish egg samples (neuston tows) were sorted for floatable
debris and the observations are summarized in Table 7-9. The debris found in
the largest quantities were toilet-paper mulch and miscellaneous plastic
pieces that could not be identified. Other debris included plastic pellets,
filaments, paint chips, and tar balls. Floatable debris found in
82
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smaller quantities included caps from crack vials, grease balls, and pieces of
styrofoam, rubber bands, paper bags, and miscellaneous metal pieces. The
neuston samples also contained an abundance of assorted seeds, but these were
not enumerated. . ..
Samples collected from the sludge plumes had larger quantities of debris than
did the background samples. For barge DB-23, the abundance of miscellaneous
plastic pieces decreased about an order of magnitude (38 per 100 m2 to 4 per
100m2) over the first 4 h after disposal. Abundance values were..too low for
the other categories and barges to show a discernable pattern.
85
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8.0 FARFIELD FATE OF SEWAGE SLUDGE
Twenty stations along three transects were occupied in and near the 106-Mile
Site for the farfield fate investigation.,- as shown in Figure 3-1. Samples
were collected from the particle maximum located in the seasonal pycnocline at
each station. The depth of the particle maximum was identified by using CTD
and transmissometry profiles generated just prior to sampling. Samples were
collected for chlorophyll a and phaeophytin, dissolved and particulate metals,
Clostridium perfringens. and particulate organic compounds. At .three of the '
stations (FA-1, FC-1, and FC-2), there was a second particle maximum at about
7 to 8 m (ca. 20 m above the seasonal pycnocline). Additional samples within
the second particulate maximum were collected at stations FC-1 and FC-2 for
Clostridium perfringens and total metals.
8.1 SLUDGE TRANSPORT BASED ON TRANSHISSOMETRY DATA
Vertical profiles of transmissometry were made at the background stations and
at all stations on the farfield transects. All raw data are archived at
Battelle. Background levels of mixed-layer turbidity in slope water, measured
at BG-21, BG-22, and BG-23, were very nearly constant at about 11%. Shelf
water at the 106-Mile Site tends to be more turbid, varying between 10% and
15%. Therefore, mixed-layer turbidity levels greater than 15% usually can be
attributed to sewage sludge. The turbidity range in -the pycnocline is higher
than in the mixed layer, with typical values between 12% and 16%. The
turbidity values measured at the pycnocline particle maxima are shown as a
contour plot in Figure 8-1. A strong signal above background turbidity is
visible at the southern end of the 106-Mile Site centered on station FA-3.
Turbidity levels at or above 18% were detected over the southern half of the
106-Mile Site and extended into the adjacent waters. This signal dropped to
background levels about 5 nmi outside the 106-Mile Site.
86
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39.4
39.2
39.0
38.8
38.6
38.4 -
38.2
-72.5 -72.3
-72.1 -71.9
LONGITUDE (*W)
-71.7 -71.5
FIGURE 8-1.
CONTOUR PLOT OF THE PYCNOCLINE PARTICLE MAXIMUM (PERCENT
TURBIDITY) FOR THE FARFIELD TRANSECTS.
87
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8.2 CLOSTRIDIUM PERFRINGENS RESULTS
Clostridium perfringens were found at only six sampling stations during the
farfield transects: FA-2, FC-1, FC-2, FCX3. FC-5 and FC-6. All of these
samples, except FC-5 and FC-6, were in the region of elevated turbidity
values. Clostridium perfringens were not found in several samples that
exhibited significantly higher turbidity values, such as FA-3. This may have
resulted from the collection of Clostridium perfringens samples at a point
above or below the measured turdidity maximum.
8.3 CHLOROPHYLL a AND PHAEOPHYTIN RESULTS
Chlorophyll a was measured as an estimate of phytoplankton biomass and primary
productivity in the farfield and the results are listed in Table C-12
(Appendix C). Chlorophyll a concentrations in the mixed layer ranged from
0.17 to 0.46 pg/L at the background stations and from 0.11 to > 2.4 ftg/L along
the farfield transects. This range is much larger than that observed for the
plume samples. A contour plot of these data (Figure 8-2) reveals a few
stations with elevated chlorophyll a concentrations (> 2 /
-------
29 ?D'N
3S 10'N
39 O'N
38 SO'N
36 40'N
38 SO'N
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Farfield
Transect
C
106-Mile Site
Farfield
Transect
A
Farfield
Transect
B
72*30' H 72*20' H 72*10' H 72* 0' H 71*50' H 71*40' V" 71*30' H
CHLOROPHYLL a 0-g/L)
FIGURE 8-2.
™E SHALLOH PARTICLE
89
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39 20'N
39 10'N
39 O'N
38'50'N
38 40'N
38*30'N
38 20'N
38 10'N
106-Mile Site
Farfield
Transect
A
Farfield
Transect
B
_L
JL
_L
-
72 30' H 72*20' H 72*10' H 72* 0' H 71*50' W 71*40*.W 71*30' H
PHAEOPHYTIN
FIGURE 8-3.
CONTOUR PLOT OF PHAEOPHYTIN AT THE SHALLOW PARTICLE MAXIMUM ON
THE FARFIELD TRANSECTS.
90
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8.4 TRACE-METAL RESULTS
The results of the dissolved and participate trace-metal, analysis for the
farfield transects are listed in Table C-10, Appendix C, and displayed
graphically for selected metals from transect FA (Figures 8-4 through 8-6)
(Figure 8-7), and FC (Figures 8-8 through 8-10). All of the metal
concentrations are elevated at Station FA-2, although the levels are well
below marine chronic WQC. Station FA-2 is at the southern end of the 106-
Mile Site, where higher turbidity and Clostidium perfringens also were
observed.
FB
Concentrations of metals in samples collected along transect FB do not
indicate any trend or elevated levels at individual stations (Figure 8-7),
The range of concentrations is close to that observed at the background
stations and is probably due to natural variability. These results are in
agreement with the absence of other sludge indicators (e.g., Clostridium
perfringens).
Concentrations of metals in samples collected along transect FC (Figures 8-8
through 8-10) indicate elevated levels occurred only at the two stations where
the second particle maximum was observed in the mixed layer (FC-1 and FC-2).
The Cu concentrations also are slightly elevated at Stations FC-5 and FC-6, in
agreement with the presence of Clostridium perfringens at the northern end of
the EC transect.
Contour plots of the trace metals did not reveal any dramatic concentration
gradients. An example is shown in Figure 8-11 for Pb, where concentrations.
were highest at the southern end of the 106-Mile Site, as expected from the
results given above.
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38 30'N
38'HO'N -
38"lO'N
-0.02
Farfield
Transect
C
T T
BG22
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106-Mile Site
Farfield
Transect
A
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Transect
B
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99
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8.5 ORGANIC CONTAMINANT RESULTS
Results of the analysis for the organic contaminants PCBs, pesticides, PAHs,
LABs, and coprostanol are listed in Tables C-14 and C-15, Appendix C. All
PAH, LAB, PCB, and pesticide compounds were either below the detection limit
or below the lowest standard (values for CL7 and CL4 are probably coeluting
compounds). Only two samples had measurable levels of a significant number of
the organic contaminants, Stations BG-21 and FA-2. The latter station also
had elevated levels of other sludge components. Coprostanol gave the best
indication of the presence of sludge for Station FA-2, with about an order-
of-magnitude increase over background. These data indicate that coprostanol
is the best organic tracer of sludge tested in this study, but is still not as
sensitive a tracer as are metals (Fe, Cu, Pb) or Clostridium perfringens.
Note that the analytical detection limits are very low for the organic
compounds (0.02 to 0.10 ng/L) and 100 L of water were filtered to obtain these
samples. Therefore, it is not likely that organic contaminants will be of
much use as sludge tracers, with the possible exception of coprostanol.
100
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9.0 CONCLUSIONS
9.1 DISCUSSION OF NULL HYPOTHESES
The 106-Mile Site Monitoring Plan ( EPA , 1992a) focuses on specific
questions or null hypotheses to evaluate the fate, transport, and effects of
sludge dumped at the 106-Mile Site. The null hypotheses that were addressed
in this survey are discussed below. The hypotheses are referenced according
to their original designation (e.g. Hn6) in the monitoring plan ( EPA ,
1992a).
9.1.1 Nearfield Fate
HQ6
HQ7
HQ8
HQ9
Sludge particles do not settle in significant quantities to the
seasonal pycnocline (50 m) in the summer or to the 50 m depth at
any time, within the Site boundaries or in the area adjacent to
the Site.
There was no evidence of accumulation of significant quantities of
sludge at the pycnocline based on the results of the chemical
analyses, microbial tracer measurements, and the transmissometry
profiles.
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.
WQC for Cu and Pb were exceeded within the site 4 h after
disposal in some of the samples. WQC were not exceeded 4 h after
disposal for Cd, Ni, and Zn. Samples were not collected 1 day
after disposal.
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.
Sludge dumped at the site can be transported outside site
boundaries before Cu and Pb are diluted below the LPC or WQC
values. All other contaminants that were measured were below
WQC. Samples were not collected 1 day after disposal, but
dilution rates indicate WQC would be met 1 day after disposal.
The disposal of sludge does not cause a significant depletion in
the dissolved oxygen content of the water column nor a
significant change in the pH of the seawater in the area.
101
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dissolved oxygen concentration did not exhibit a significant
difference from background levels for any of the profiles
collected. The pH of the samples was within the marine WQC ranqe
and did not change significantly for any samples.
9.1.2 Short-Term Effects
HQ10
H011
HQ13
HQ15
No significant biological effects in the water column are measurable
within the site within 1 day after disposal.
Results of mysid and zooplankton toxicity tests performed on plume
samples collected 4 h after disposal were either inconclusive or
indicated no toxic effects.
The results of the sea urchin fertilization tests indicated that
fertilization rates decreased immediately after disposal, but 4 h
after disposal there was no decrease in the fertilization rate
u1.-,1sl? eggs were found in the neuston samples collected 'at
the 106-Mile Site, probably because of the time of the year. No
chromosomal abnormalities were observed in the eggs.
No increase in primary productivity or any changes in
planktonic biomass or species composition will occur.
Direct measurement of primary production and plankton abundance/
speciation were not performed. Chlorophyll a and phaeophytin were
measured as indicators of plankton biomass and health. The results
were inconclusive because elevated phaeophytin concentrations were
found in nearly all of the samples, possibly due to an interference
in the analytical method from pigments in the sludge.
Sludge constituents do not accumulate in the surface microlaver
in the vicinity of the Site.
Although this hypothesis was included in the original
survey objectives, surface micro layer sampling could not
be performed because of the sea conditions. '
9.1.3 Farfield Fate
Ocean currents .do not transport sludge to any adjacent shorel-ine
beach, marine sanctuary, fishery; or shellfishery. '
There was no evidence of sludge transport to the shoreline or any
fishery area, although the amount of data is not yet sufficient to
conclusively support this hypothesis.
102
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Sludge recirculation through the Site is not significant.
The results of the chemical analyses and current observations were
inconclusive with respect to the potential for sludge to recirculate
through the 106-Mile Site. There was significant mixing of shelf
water and slope water in the upper 10 m during the survey. This
made it difficult to predict the movement of sludge outside the
Site.
9.2 EVALUATION OF SLUDGE TRACERS
The results of the chemical contaminant analyses, microbial measurements, and
turbidity profiles provided a broad and complimentary data set to estimate
sludge dilutions and track the transport of sludge in the farfield. However,
it is apparent that certain sludge tracers are a more sensitive and cost-
effective means of detecting sludge than others.
9.2.1 Turbidity Profiles
The transmissometry profiles obtained with the BOSS provided very low cost,
real-time tracking of sludge plumes that are invaluable in measuring the
extent of plume advection and locating sample collection positions. The
turbidity profiles do not provide the resolution necessary to accurately
calculate sludge dilutions, but do allow reasonable estimates of sludge
dispersion. Transmissometry profiles appear to be effective in evaluating the
farfield transport of sludge because the elevated turbidity values observed
along the farfield transects correlated well with other tracer measurements,
with a few exceptions. These exceptions could.be "false positives" caused"by
the nonselective nature of turbidity measurements, but could also result from
collection of chemical tracer samples at a point above or below the particle
maximum (yeilding a sample with a lower contaminant concentration).
.9.2.2 Trace-Metal Measurements
In the plume samples, trace metals were a sensitive indicator of the sludge
concentration and, therefore, the metals results allowed an accurate
103
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estimation of sludge dilution. The Fe data were highly correlated with the
data for Cu, Pb, and Zn. A weaker correlation was found with Ni and Cd, and
no correlation was found with TSS. This indicates that Fe measurements alone
could provide rough estimates of sludge dilution or could be used as a
screening tool for a tiered analytical approach. However, Cu measurements are
probably the best metal tracer of sludge because they provide better precision
and are directly comparable to marine WQC.
There are insufficient data to fully evaluate the effectiveness,of metals as a
tracer for sludge in the farfield. The metals were distributed primarily in
the dissolved phase, with only a small fraction bound to particles. The few
samples that had elevated concentrations of metals also had elevated
particulate indicators of sludge (i.e., turbidity and Clostridium
perfringens). There were several samples that contained nonmetal, particulate
sludge indicators, but did not have elevated metal concentrations. This
discrepancy could have resulted from a faster dilution of dissolved metals
relative to the particulate bound indicators. The partitioning behavior of
metals after sludge disposal and the relative dilution rates of particulate
and dissolved metals needs to be investigated more thoroughly to
evaluate the effectiveness of metals as a tracer for sludge in the farfield.
1 *• j
9.2.3 Clostridium Perfrinoens
Clostridium perfringens were found in only six samples along the farfield
transects, most of which also displayed elevated turbidity. It is apparent
that Clostridium perfringens and turbidity profiles are well correlated and
both provide-rapid, low-cost data to track sludge movement. However, no
empirical relationship has been established between Clostridium perfringens
and pathogens and, therefore, these results should be used for sludge tracking
purposes only.
104
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9.2.4 Organic Contaminants and Tracers
The concentrations of PAHs, LABs, PCBs, and pesticides were either below the
detection limit or below the lowest standard for all samples and, therefore,
were not effective as sludge tracers in this study. Coprostanol gave the best
indication of the presence of sludge, with about an order-of-magnitude
increase over background for Station FA-2. These data indicate that
coprostanol is the best organic tracer of sludge tested in this study and
could be used as a screen for the other organic contaminants. However,
coprostanol is not as sensitive a tracer as are metals (Fe, Cu, Pb) or
Clostridium perfringens, and it is a more expensive analysis.
105
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10.0 REFERENCES
Battelle. 1988. Phase 4 Work/Quality Assurance Project Plan for the
National Status and Trends Mussel Hatch Program. Prepared for
NOAA by Battelle Oceans Sciences. Contract No. 50-D6NC-5-00263.
Bisson, J.W. and V.J. Cabelli. 1979. Membrane Filter Enumeration
Method of Clostridium perfrinoens. Appl. Environ. Microbiol.
37:55—66.
Danielsson, L., 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.
Eganhouse, R.P., E.C. Ruth, and I.R. Kaplan. 1983. Determination of
Long-Chain Alkylbenzenes in Environmental. Samples by Argentation
Thin-Layer Chromatography/High. Resolution Mass Spectrometry and
Gas Chromatography/Mass Spectrometry. Anal. Chem. 55:2120-2126
EPA.
EPA.
EPA.
EPA.
EPA.
EPA.
EPA.
1978. Bioassay Procedures for the Ocean Disposal Permit Program
U.S. Environmental Protection Agency. EPA/600/9-78-010.
1986. Quality Criteria for Water 1986. U.S. Environmental
Protection Agency Office of Water Regulations and Standards.
EPA/440/5-86-001.
1987. 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 (formerly OMEP), Washington, DC.
1988a. Short-Term Methods for Estimating the Chronic Toxicity of
Effluents and Receiving Waters to Marine and Estuarine Organisms.
U.S. Environmental Protection Agency. EPA/600/4-87/028.
1988b. Final Report for Nearfield Fate Monitoring at the 106-Mile
Deepwater Municipal Sludge Site: Winter 1988 Oceanographic Survey
March 1-5, 1988. Environmental Protection Agency Oceans and
Coastal Protection Division (formerly OMEP), Washington, DC.
1988c. Final Survey Plan for Summer 1988 Oceanographic Survey to
the 106-Mile Site September 10-17, 1988. Environmental Protection
Agency Oceans and Coastal Protection Division (formerly OMEP1
Washington, DC. "
1988d. Initial Survey Report for Summer 1988 Oceanographic Survey
to the 106-Mile Site September 10-17, 1988. Environmental
Protection Agency Oceans and Coastal Protection Division fformerly
OMEP), Washington, DC.
106
-------
EPA. 1992a. Final Draft Monitoring Plan for the 106-Mile Deepwater
Municipal Sludge Site. Environmental Protection Agency. EPA 842-
S-92-009.
EPA.
EPA.
EPA.
1992b. Final Draft Implementation Plan for the 106-Mile Deepwater
Municipal Sludge Site Monitoring Program. Environmental
Protection Agency. EPA 842-S-92-010.
1992c. Final Report for Nearfield Monitoring of Sludge Plumes at
the 106-Mile Deepwater Municipal Sludge Site: Results of-a Survey
Conducted August 31 through September 5, 1987. Environmental
Protection Agency. EPA 842-S-92-004.
1992d. Determination of Sludge Dumping Rates for the 106-Mile
Site. Environmental Protection Agency. EPA 842-S-92-006.
Longwell, A.C., and J.B. Hughes. 1980. Cytological, Cytogenetic, and
Developmental State of Atlantic Mackerel Eggs from Sea Surface
Waters of the New York Bight, and Prospects for Biological
Monitoring with Ichthyoplankton. Rapp. Reun. Cons. Int Explor.
Mer. 179:257-291.
Peltier, W.H., and C.I. Weber. 1985. Methods for Measuring the Acute
Toxicity of Effluents to Freshwater and Marine Organisms. U.S.
Environmental Protection Agency. EPA 600/4-85/013.
Stumm, W., and J.J. Morgan. 1981. Aquatic Chemistry, 2nd edition, John
Wiley, New York, NY. 780 pp.
107
-------
Appendix A
QUALITY CONTROL DATA
-------
TABLE A-l. RESULTS OF ANALYSIS OF DUPLICATE SAMPLES.
Sample ID
AAJ785-23
AAJ724rla
AAJ729°
AAJ754&
AAJ77313
Cd
18
10
20
39
12
Relative Percent Difference (RPD)
Cu Fe Ni Pb
17 13 25 23
3 2 49 4
2 20 3 3
5 15 NAC 32
2 24 NA 1
Zn
50
3
18
NA
NA
Whole water sample.
Filtered sample.
Not analyzed.
A-l
-------
TABLE A-2. RESULTS OF FILTER BLANKS ANALYZED WITH TRACE-METAL SAMPLES.
Sample ID
Filter Blanks (ng)
Cd
Cu
Fe
Pb
Zn
GK25-FIB
GK26-FIB
AAJ745-FIB
AAJ746-FIB
AAJ759-FIB
AAJ760-FIB
0.165
0.250
0.590
0.595
1.080
1.235
<3.20
<3.20
2.10
1.15
<1.10
<1.10
10.5
<4.5
17.0
16.0
19.5
<8.5
5.45
6.25
NAa
NA
NA
NA
1.15
1.35
1.495
<0 . 690
0.945
<0.690
23.60
12 35
NA
NA
NA
NA
Not analyzed.
A-2
-------
TABLE A-3. RESULTS OF PROCEDURAL BLANKS FOR TRACE-METAL ANALYSES.
Sample ID
GI34-PB
6I35-PB
6I38-PB
GI39-PB
GK29-PB
GK30-PB
GK33-PB
GK34-PB
GK37-PB
GK38-PB
Procedural Blanks (ng)
Cd
0.88
1.00
0.92
0.94
1.46
1.36
1.02
1.32
0.72
0.76
Cu
<6.2
<6.2
<3.2
<3.2
<1.68
<1.68
<1.48
<1.48
<1.46
-------
TABLE A-4. PERCENT RECOVERY OF METALS FROM CERTIFIED STANDARD
REFERENCE MATERIAL ANALYZED WITH EACH BATCH
Sample ID
Recovery (%)
Cd
Cu
Fe
Ni
Pb
Zn
GI32-SRM
6I33-SRM
GI36-SRM
GI37-SRM
GK27-SRM
GK28-SRM
GK31-SRM
GK32-SRM
GK35-SRM
GR36-SRM
97
100
100
69
111
104
90
91
90
78
111
129
103
102
112
113
94
. . 93
94
87
308
277
268
196
134
123
102
111
778
138
109
109
136
121
113
109
NAa
NA •
NA
NA
95
105
105
92
95
95
90
82
' 91
86
180
107
96
73
/ «J
80
.88
NA
NA
iin
NA
NA
Not analyzed.
A-4
-------
TABLE A-5. PERCENT RECOVERIES OF METALS FROM SAMPLES SPIKED
WITH KNOWN AMOUNTS OF METAL
Sample ID
Recovery (%)
Cd
Cu
Fe
Ni
Pb
Zn
AAJ785-2
AAJ724-1
AAJ729
AAJ754
AAJ773
109
38
100
95
90
112
100
98
109
106
107
101
100
98
130
102
41
100
NAa .
NA
116
102
96
114
100
118
100
96
NA
NA
Not analyzed.
A-5
-------
TABLE A-6. METHOD DETECTION LIMITS (MDL) FOR ANALYSIS OF
SAMPLES FOR TRACE METALS.
Metal
Cadmium
Copper
Iron
Nickel •
Lead
Zinc
Method Detection
Participate3
- te/L)
0.0001
0.0032
0.0090
0.0064
0.0018
0.0110
Limit
Dissolved5
(/»g/U
0.002
0.009 H
0.034
. 0.025
0.006
0.003
MDL = (instrument det. limit)(extract vol)/(l L filtrate vol).
MDL = (instrument det. limit)(extract vol)/(200 mL sample vol),
A-6
-------
TABLE A-7. SURROGATE PERCENT RECOVERIES FOR PAHa
AND LAB.D
Sample ID
HV10 PB
AAJ338
AAJ339
AAJ349
AAJ356
AAJ357
AAJ360
AAJ362
AAJ365
AAJ365
AAJ368
AAJ371
AAJ377
AAJ379
AAJ381
AAJ383
AAJ437
AAJ438
AAJ446
AAJ449
d8-N
46
61
72
86
84
82
82
94
85
85
83
79
64
90
111
54
104
94
138C
115
dlO-A
61
77
99
100
104
108
108
109
97
97
102
109
86
112
129
59
120
103
146C
123
d!2-P
88
112
118
124
108
119
107
107
113
113
116 .
101
114
122
128
106
111
118
124
17C
1-PN
55
38C
45
93
111
33C
120
117
80
80
116
133C
101
97
145C
19C
139C
47
89
53
a PAH Surrogates
d8-N: d8-naphthalene ~
dlO-A: dlO-acenaphthene
d!2-P: d!2-perylene
b LAB Surrogate
1-PN: 1-phenyl nohane
c Value is outside the acceptable recovery range (40% - 130%).
A-7
-------
TABLE A-8. PROCEDURAL BLANK RESULTS AND MATRIX SPIKE (MS), MATRIX
SPIIJ
82
\J£-
85
-------
TABLE A-9. PROCEDURAL BLANK (PB) AND PCB/PESTICIDE-COPROSTANOL MATRIX SPIKE
(MS) AND MATRIX SPIKE DUPLICATE (MSD) RECOVERIES (%).
Analyte
CL2(08) .
HCB
Lindane
CL3(18)
CL3(28)
Heptachlor
CL4(52)
Aldrin
CL4(44)
Heptachlorep
CL4(66)
OPDDE
CL5(101)
A CH
Transnonachlor
Dieldrin
PPDDE
OPDDD
CL5(118)
PPDDD
OPDDT
CL6(153)
CL5(105)
PPDDT
CL6(138)
CL7(187)
CL6(128)
CL7(180)
Mi rex
CL7(170)
CL8(195)
CL9(206)
CL10(209)
Coprostanol
PB
(ng)
NDb
NO
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
0.4
0/9
ND
0.8
ND
ND
ND
MS
91
98
111
93
113
. 86
101
145C
110
. 90
107
122
99
122
114
104
127
107
109
130
112
100
• 118
118
113
105
116
112
111
147C
114
115
110
84
Percent
MSD
81
71
136C
81
127
110
102
162C .
121
106
114
122
75
140C
141C
148C -
147C
104
109
167C
154C
97
149C
130
101
108
137C
123
128
190C
130
122
102
• 98
Recovery
Mean
86
85
124
87
120
98
101
153
,116
98 .
•no
122
87
131
127
126
137
106
109
149
133
98
134
124
107
107
127
117
'120
169
122
119
106
91
RPDa
11
32
20
14
11
25
1
• 11
9.
16
6
0
27
14
21
35
14
3
1
25
32
4
23
9
11
3
16
9
15
25
14
6
7
14
aRPD: 2 * [(MS - MSD)/(MS + MSD)] * 100.
bND: Not detected.
cValue is outside the acceptable recovery range (40% -- 130%)
A-9
-------
TABLE A-10. SURROGATE RECOVERIES (V) FOR .
PCB/PESTICIDE3 AND COPROSTANOL.b
Sample ID
HV10 PB
AAJ338
AAJ339
AAJ349
AAJ356
AAJ357
AAJ360
AAJ362
AAJ365
AAJ368
AAJ371
AAJ377
AAJ379
AAJ381
AAJ383
AAJ437
AAJ438
AAJ446
AAJ449
DBOFB
67
53
97
76
82
57
78
73
74
82
74 .
73
75
84
27c
76
51
81
50-
Androstanol
78
71
23C
83
74
67
73
77
71
80
91 . •
' . 74
88
75
86
71
81
83
79
a PCB/Pesticide surrogate is DBOFB.
Coprostanol surrogate is androstanol.
c Value is outside the acceptable range (40% - 130%)
A-10
-------
Appendix B
FIELD DATA FOR MONITORING ACTIVITIES
CONDUCTED AT THE 106-MILE SITE SEPTEMBER 9-20, 1988
-------
-------
TABLE B-l. SUMMARY OF TOW INFORMATION FOR HORIZONTAL PROFILING ACTIVITIES CONDUCTED AT
THE 106-MILE SITE DURING THE SUMMER 1988 SURVEY
Survey Date
Tow T=0 Hours Number Start Tow
Depth (h) Towing of Lat. (N) Long.(W)
(m) Tows
End Tow
Lat. (N) Long. (Wj
DB-21 9-16-88 5-14 1855 9
DB-22. 9-17-88 2-10 1923 4.5
DB-23 9-18-88 2-25 2245 7
24 38°57.50' 72°04.20' 38°56.83' 72°07.50'
9 38°57.90' 72°03.18' 38°56.81' 72°03.60'
18 38°52.09' 72°00.43' 38°50.57' 71°58.18'
B-l
-------
TABLE B-2. SUMMARY OF ORGANIC SAMPLES COLLECTED FROM THE SEWAGE PLUMES SAMPLED AT
THE 106-MILE SITE DURING THE SUMMER 1988 SURVEY
Station Latitude Longitude Date Time Time Depth Rep.
(N) . (W) Delta No.
(h) (n)
Total Part
Organic Organic3
DB-20
DB-21
DB-21
DB-21
DB-21
DB-21
DB-21
DB-2L
DB-22
DB-22
DB-22
DB-22
DB-23
DB-23
DB-23
DB-23
DB-23
38°45.84'
38° 56. 68 '
38°56.38'
38°56.16'
38°55.93'
38°56.13'
38°56
38°56
38°57
38°57
38°57
38°57
38°52
38° 52
38° 52
38°52
38°52
.02'
.10'
.90'
.78'
.44'
.01'
.09'
.88'
.68'
.50'
.52'
72°00.40'
72°04.15'
72°04.35'
72°04.84'
72°04.86'
72°04.70'
72°04.
72°04.
72°03.
72°03.
72°03.
72°03.
72°00.
72°00.
72°00.
71°59.
71°58.
68'
60'
18'
08'
or
04'
43'
47'
26'
73'
66'
09/11
09/16
09/16
09/16
09/16
09/17
09/17
09/17
09/17
09/17
09/17
09/17
09/18
09/18
09/19
09/19
09/19
1456
1906
2015
2216
2310
0014
0211
0342
1924
2040
2133
2251
2249
2345
0047
0149
0309
0
0
1
3
4
5
7
8.5
0
1.2
2.2
3.5
0
1
2
3
4.4
5
2
7
5.5
5.5
5
2
1.5
3
3
2.8,
2.5
2
4.5
4.5
4
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TABLE B-6 SUMMARY OF XCP (EXPENDABLE CURRENT PROFILER) ANDHYDRO BALL TIMES OF
DEPLOYMENT, PROFILE DEPTHS, AND STATIONS OCCUPIED AT THE 106-MILE
SITE DURING THE SUMMER 1988 SURVEY
Station
Date
Time Profi1e Depth
(h) (•)
Lat.
(N)
Long.
(W)
XCP-20
HB-1
9-11-88
9-16-88
0630
1658
1500
250
39°09'
39°03.7
72°03'
72°03.7'
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-------
TABLE B-9. SUMMARY OF CTD PROFILES TAKEN AT ALL FARFIELD STATIONS DURING THE
SUMMER 1988 SURVEY
Station
FA-1
FA-2
FA-3
FA-4
FA-5
FA-6
FA-7
FB-1 .
FB-2
FB-3
FB-4
FB-5
FB-6
FB-7
FA-1A
FC-1
FC-2
FC-3
FC-4
FC-5
FC-6
Date
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/19
09/19
09/19
09/19
Time
0040
0135
0232
0337
0457
0606
0707
1346
1244
1142
1036
0948
0851
0800
1710
1825
1931
0737
0832
0928
1035
Depth
(m)
40
40
44
46
47
41
45
44
45
42
45
47
48
49
45
42
50
43
43
45
44
Lat.
(N)
38°49.83'
38°45.05'
38°40.00'
38°35.04'
38°30.12'
38°25.06'
.38°20.01'
38°50. 30'
38°45.05'
38°40.00'
38°35.06'
38°30.07'
38°25.07'
38°20.00'
38°49.99'
38°50.00'
- 38°54.93'
39°00.04'
39°05.03'
39°10.12'
39°14.99'
Long.
(W)
72°02.47'
72°02.53'
72°02.49'
72°02.45'
72°02.47'
72°02.24'
• '72°02.51'
71°56.07'
71°55.90'
71°55.87'
71°55.99'
71°55.97'
71°56.05'
71°55.74'
72°02.55'
72°09.08'
72°08.90'
72°09.04:'
72°08.95'
72°08.98'
72°09.18'
B-9
-------
TABLE B-10.
SUMMARY OF ORGANIC SAMPLES COLLECTED FROM THE BACKGROUND
AND FARFIELD STATIONS IN THE VICINITY OF THE 106-MILE SITE
DURING THE SEPTEMBER 1988 SURVEY.
Station
B6-21
BG-21
BG-21
BG-22
BG-22
BG-22
FA-1
FA-1
FA-2
FA-2
FA-3
FA-3
FA-4
FA-4
FA-5
FA-5
FA-6
FA-6
FA-7
FA-7
FB-7
FB-7
FB-6
FB-6
FB-5
FB-5
FB-4
FB-4
FB-3
FB-3
FB-2
FB-2
FB-1
FB-1
FA-1 -A
FA-1 -A
FC-1
FC-1
FC-2
FC-2
FC-3
FC-3
FC-4
FC-4
FC-5
FC-5
FC-6
FC-6
Lat.
(N)
39°04.55'
39°03.99'
39°03.99'
39°12.96'
39°12.96'
39°13.19'
38°49.80'
38°49.80'
38°44.98'
38°44.98'
38°40.09'
38°40.09'
38°35.li'
38C35.11'
38°30.04'
38°30.04'
38°25.05'
38°25.05'
38°20.22'
38°20.22'
38°20.18'
38°20.18'
38°25.07'
38°25.07'
38°30.03'
38°30.03'
38°35.05'
38°35.05'
38°40.00'
38°40.01'
38°45.10'
38°45.10'
38°50.26'
38°50.26'
38°49.99'
38°49.99'
38°50.00'
38°50.00'
38°54.93'
38°54.9"3'
39°00.03'
39°00.03'
39°05.03'
39°05.03'
39°10.12'
39°10.12'
39°14.99'
39°14.99'
Long.
(W)
72°02.90'
72°03.72'
72°03.72'
72°02.98'
72°02.98'
72°03.12'
72°02.46'
72°02.46'
72°02.52'
72°02.52'
72°02.53'
72°02.53.'
72°02.43'
72°02.43'
72°02.03'
72°02.03'
72°02.23'
72°02.23'
72°02.35'
72°02.35'
71°55.40'
71°55.40'
71°55.80'
71°55.80'
71°55.94'
71°55.94'
71°55.88'
71°55.88'
71°55.87'
71°55.87'
71°55.68'
71°55.68'
71°56.09'
71°56.09'
72°02.55'
72°02.67'
72°09.08'
72°09.08'
72°08.90'
72°08.90'
72°09.05'
72°09.05'
72°08.95'
72°08.95'
72°08.98'
72°08.98'
72°09.15'
72°09.15'
Date
09/16
09/16
09/16
09/17
09/17
09/17
09/18
09/18
09/18
09/18
09/18
0,9/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/18
09/19
09/19
09/19
09/19
09/19
09/19
09/19
09/19
Time
1459
1528
1528
1622
1622
1643
0041
0041
0145
0145
0246
0246 '
0355
0355
0506
0506
0628
0628
0717
0717
0810
0810
0903
0903
0953
0953
1054
1054
1148
1148
1250
1250
1352
1352
1731
1731
1834
1834
1946
1946
0743
0743
0839
0839
0936
0936
1043
1043
Depth
(m)
10
32
32
34.5
34.5
8
34
34
21
20 •
33
33
26
26
27
27
28
28
14
14
37
37
25
-25
22
22
24
24
27
27
26
26
31
31
29
29
28
28
26
26
33
33
36
36
29
29
21
21
Rep.
No.
1
1
2
1
2 '
1
1
2
1
2
1
2
1
2
1
2
1
2
1
2
1
2
1
2
1
2
1
2
1
2
1
2
1
2
1
2
1
2
1
2
1
'2
1
2
1
2
1
1
Total
Organic
1
0
0
0
0
1
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
Part
Organic
0
1
1
1
1
0
1
1
1
1
1
•1-
1
• 1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
B-10
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-------
Appendix C
ANALYTICAL RESULTS FOR TRACE METALS AND ORGANIC COMPOUNDS
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TABLE C-4. COPPER CONCENTRATIONS IN SLUDGE AND SEAWATER AND DILUTION FACTORS
FOR SEWAGE PLUMES STUDIED IN SEPTEMBER 1988.
Plume
DB21
Princess B
DB22
Spring Creek
DB23
Lemon Creek
Sample Time
(h)
Sludge
0
1
3
4
5
7
9
Sludge
0
• 1 • •
2
3
Sludge
0
1
2
3
4
7
Cu
0*g/L)
15,000 ± 1600a
8.7°
5'4h
2.3b
4.0C
2.2C
2.8C
2.5C
45,OOQb
8.4B
1.9C
1.5C
0.34C
66,OOQb
8.45
12. 7C
11. 3C
11. Oc
9.5C
5.9C
Dilution
Factor
0
1,700
2,800
6,500
3,800
6,800
5,400
6,000
0
5,400
•24,000
30,000
130,000
0
7,900
5,200
5,800
6,000 '
6,900
11,000
a Mean of triplicate analysis ± standard deviation
Single sample.
c Mean of duplicate analysis.
C-4
-------
TABLE C-5. CADMIUM CONCENTRATIONS AND DILUTION FACTORS FOR SEWAGE PLUMES
STUDIED IN SEPTEMBER 1988.
Plume
DB21
Princess B
DB22
Spring Creek
DB23
Lemon Creek
•
Sample Time
(h)
Sludge
0
1
3
4
5
7
9
Sludge
0
1
. 2-
3
Sludge
0
1
2
3
4
7
Cd
ta/L)
530 ± 60a
0.44°
0.26°
0.09°
0.19C
O.llc
0.14C
0.13C
230° .
0.13°
0.03C
0.03C
0.01C
680° .
0.48b
0.13C
0.12C
0.12C
O.llc
0.07C
Dilution
Factor
0
1200
2000
5900
2800
4800
3800
4100
0
1800
7700 •
7700
23,000
0
1400
5200
5700
5700
6200
9700
a Mean of triplicate analysis ± standard deviation.
Single sample.
c Mean of duplicate analysis.
C-5
-------
TABLE C-6. IRON CONCENTRATIONS AND DILUTION FACTORS FOR SEWAGE PLUMES STUDIED
IN SEPTEMBER 1988.
Plume
DB21
Sample Time
(h)
Sludge
Princess B 0
DB22
Spring
DB23
1
3
4
5
7
9
Sludge
Creek 0
1
• 2
3
Sludge
Lemon Creek 0
a Mean
b Sing!
c Mean
1
2
3
4
7
of triplicate analysis ±
e sample.
of duplicate analysis.
Fe
OMJ/L)
120,000 ± 18,000a
106°
71K
29b
73C
33C
46C
41c
500,OQOb
71
13C
llc
2c
450,000b
45B
61C
52C
51C
73C
43C
standard deviation.
Dilution
Factor
0
1100
1700
4100
1600
3600
2600
2900
0
7000
38,000
45,000
250,000
0
10,000
7400
8700
8800
6200
10,000
C-6
-------
TABLE C-7. LEAD.CONCENTRATIONS AND DILUTION FACTORS FOR SEWAGE PLUMES STUDIED
IN SEPTEMBER 1988.
Plume
DB21
Princess B
DB22
Spring Creek
DB23
Lemon Creek
Sample Time
(h)
Sludge
0
1
3
4
5
7
9
Sludged
0
1
2
'3
Sludge
0
1
2
3
4
7
Pb
0*/L)
15,300 ± l,700a
15.8°
9-8h
3.5°
7.3C
3.7C
4.8C
4.4C
14,000°
2.8B
0.6C
0.4C
.. O.lc
78,000°
12.9°
17. 2C
15. 4C
15. 4C
13. 8C
8.4C
Dilution
Factor
0
970
1600
4400
2100
4100
3200
3500
0
5000
23,000
35,000
140,000
0
6000
4500
5100
5100
5600
9300
Mean of triplicate analysis ± standard deviation.
Single sample.
Mean of duplicate analysis.
C-7
-------
TABLE C-8. ZINC CONCENTRATIONS AND DILUTION FACTORS FOR SEWAGE PLUMES STUDIED
IN SEPTEMBER 1988.
Plume
DB21
Princess B
DB22
Spring Creek
DB23
Lemon Creek
Sample Time
(h)
Sludge
0
1
3
4
5
7
9
Sludge
0
1
2
3
Sludge
0
1
2
3
4
7
Zn
te/ir
80,000 ± 8,800a
66.5°
43. 5 J
13. 3b
29. 8C
14. 9C
18. 7C
16. 5C
37,000b
13. 4B
3.0C
2.1C
0.6C
57fOO~Ob
8.6*
13. 2C
U'7r
11. Oc
13. 4C
8.7C
Dilution
Factor
0
1200
1800
6000
2700
5400
4300
4800
0
2800
12,000
18,000
. 62,000
0
6600
4300
4900
5200
4300
6600
Mean of triplicate analysis ± standard deviation-.
Single sample.
c Mean of duplicate analysis.
C-8
-------
TABLE C-9. TOTAL SUSPENDED SOLIDS (TSS) CONCENTRATIONS AND DILUTION FACTORS
FOR SEWAGE PLUMES STUDIED IN SEPTEMBER 1988
Plume
DB21
Princess B
DB22
Spring Creek
DB23
Lemon Creek
Time
(h)
Sludge
0
1
3
4
5
7
9 . ' •
Sludge
0
1
2
3
Sludge
0
1
2
3 '
4
7
TSS
(mg/L)
15,100
14.97
11.84
4.33
8.55
6.49
4.63
4.27
5,400
2.90
0.74
0.43
0.08
2,900
3.47
3.38
2.56
- 2.10
1.23
1.00
Dilution
Factor
0
1,000
1,300
3,500
1,800
2,300
3,300
3,500
0
1,900
7,300
13,000
68,000
0
800
900
1,100
1,400
2,400
2,900
Background
0 - 0.5
C-9
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TABLE C-ll.
RESULTS OF TOTAL METAL ANALYSES FOR FARFIELD
AND BACKGROUND SAMPLES (/ig/L)
Sample ID
AAJ779
AAJ783
AAJ765-1
AAJ765-2
AAJ723-1
AAJ723-2
Station
FC-1
FC-2
BG-21
BG-21
BG-22
BG-22
Depth
7
8
10
10
8
8
(m) Date
09/18/88
09/18/88
09/16/88
09/16/88
09/17/88
09/17/88
Cd
0.013
0.010
0.003
0.007
0.005
0.005
0
0
0
0
0
0
Cu
.261
.295
.138
.147
.124
.125
1
2
0
1
0
0
Fe
.569
.623
.900
.008
.409
.357
0
0
0
0
0
0
Pb TSS
.127
.122
.014
.014
.014
.015
(mg/L)
NAa
NA
0.990
0.990
NDB
ND
? Not available.
D Not detected.
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C-15
-------
TABLE C-13.
SUMMARY OF AMMONIA AND pH DATA FROM
PLUME-TRACKING EVENTS AT THE 106-MILE
SITE IN THE SUMMER 1988 SURVEY.
Station
DB-20
DB-21
DB-21
DB-21
DB-21
DB-21
DB-21
DB-21
DB-22
DB-22
DB-22
DB-22
DB-23
DB-23
DB-23
DB-23
DB-23
BG-21
BG-21
BG-22
BG-22
Time
(h)
0
0
1
3
4
5
7
9
"o
1
2
3
0
1
2
3
4
NA
NA
NA
NA
Depth
(»)
5
3
7
5.5
5.5
5
2
1.5
3
3
2.8
2.5
4
4.3
4.5
4
12
10
33
33
8
NH-,
(mg/C)
NAa
0.28
0.19
0.23
0.13
0.21
0.31
0.1
0.10
0.18
0.14
0.04
<.01
0.09
0.25
0.16
0.12
O.10
O.10
0.22
0.19
PH
NA
8.01
7.95
8.17
8.13
8.09
8.03
8.14
8.38
8.21
8.24
8.27
8.30
8.25
8.27
8.22
8.22
8.24
8.20
8.11
8.24
Not available.
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0.500
0.400 -4-
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0.300
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0.100 *
i
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O
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t
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4 6
TIME AFTER DISPOSAL, h
4 6
TIME AFTER DISPOSAL,-*!
10
DB22
10
DB23
0.000
4- 6
TIME AFTER DSPOSAL, h
10
FIGURE C-l. PLOTS OF CADMIUM CONCENTRATIONS IN THE SLUDGE PLUME VERSUS
TIME FOR PLUMES DB-21, DB-22, AND DB-23. MARINE WATER QUALITY
CRITERIA FOR CADMIUM ARE ACUTE: 43 /*g/L; CHRONIC: 9.3 /*g/L.
C-21
-------
20
15 -- .
o>
* 10 +
DB21
20
4 6
TIME AFTER DISPOSAL, h
10
15 --
10
£
DB22
20
4 6
TIME AFTER DISPOSAL,
10
15 + '
£
.10 +
£
5--
DB23
4 5
TIME AFTER DISPOSAL, h
10
FIGURE C-2.
PLOTS OF LEAD CONCENTRATIONS IN THE SLUDGE PLUME VERSUS TIME
FOR PLUMES DB-21, DB-22, AND DB-23. MARINE WATER QUALITY
CRITERIA FOR LEAD ARE ACUTE: 140 /tg/L; CHRONIC: 5.6 /ig/L.
C-22
-------
1.500
1.000 -!-
I i
2 0.500 -i-
DB21
0.000
1.500
1.000 --
01
3.500 -L--
4 6
TIME AFTER DISPOSAL, h
10
D822
0.000
1.500
4 -6
TIME AETER DISPOSAL, h
10
DB23
1.000
o>
0.500
t
o.ooo
4 6
TIME AFTER DISPOSAL, h
10
FIGURE C-3.
PLOTS OF NICKEL CONCENTRATIONS IN THE SLUDGE PLUME VERSUS TIME
FOR PLUMES OB-21, DB-22, AND DB-23. MARINE WATER QUALITY
CRITERIA FOR NICKEL ARE ACUTE: 75 /ig/L; CHRONIC: 8.3 pg/L.
C-23
-------
70 y
60 --
50 --
40 --
30--
20--
10^
0 - —
70
60--
4 6
TIME AFTER DISPOSAL, h
10
50 --
1 40 +
15
30--
20--
10
0
DB22
70
60--
50 --
40
30 --
20 +
10
0
4 . 6
TIME AFTER DISPOSAL, h
10
DB23
4 6
TIME AFTER DISPOSAL, h
10
FIGURE C-4.
PLOTS OF ZINC CONCENTRATIONS IN THE SLUDGE PLUME VERSUS TIME
FOR PLUMES DB-21, DB-22, AND DB-23. MARINE WATER QUALITY
CRITERIA FOR ZINC ARE ACUTE: 95 /tg/L; CHRONIC: 86 /ig/L.
C-24
-------
TOO
• 80 --
60 4-
40
20
0
DB21
4 6
TIME AFTER DISPOSAL, h
10
100 -j-
80 -|-
"^60-4-
* •
,« T
- 40 +
. 20 +
,1
DB22
4 - 6
TIME AFTER DISPOSAL, h
10
100 -4-
T
80 4-
20
0
DB23
4 6
TIME AFTER DISPOSAL, h
FIGURE C-5. PLOTS OF IRON CONCENTRATIONS IN THE SLUDGE PLUME VERSUS TIME
ARE N° MRINE HATER
C-25
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Appendix D
ASSESSMENT OF CETACEANS AND SEABIRDS
-------
ASSESSMENT OF CETACEANS AND SEABIRDS
Contract No. K2202(8873)-700
Work Assignment 118
Prepared by
P. Michael Payne and Bert Nickerson
Marine Mammal and Seabird Studies
Manomet Bird Observatory
Box 936
Manomet, MA 02345
for
BATTELLE MEMORIAL INSTITUTE
Duxbury Operations
397 Washington Street
Duxbury, MA 02332
(617) 934-0571
D-l
-------
TABLE OF CONTENTS
Page
LIST OF FIGURES ,. . . i
LIST OF TABLES . . f
INTRODUCTION j
Study Area .2
METHODS o2
Sampling Technique 02
Analyses of Census Data 4
RESULTS AND DISCUSSION . . ............. .5
Cetaceans ..........;... .5
Marine Turtles. ..,...' .9
Seabirds g
Cetacean Sightings Relative to the 106-Mile Site .9
LITERATURE CITED .9
D-2
-------
Figure 1.
Figure 2.
LIST OF FIGURES
Location of the Deepwater Dutnpsite-106 and the North
Atlantic Incineration Site
Location of Cetacean Sightings Observed Aboard the OSV
Peter H. Anderson. September 9 through 20, 1988 . . . .
.3
.8
Table 1.
Table 2.
Table 3.
LIST OF TABLES
List of all Marine Mammal Observations in Slope and Shelf
Edge Haters During the Baseline Survey to the Deepwater
Dumpsite 106, September 9 through 20, 1988
Relative Abundance (SE) of Cetaceans by Species Observed
in Slope and Shelf-Edge Haters, and the Number of 15-min
Transects Conducted Aboard the OSV Peter H. Anderson
During the Baseline Survey to Deepwater Dumpsite-106,
September 9 through 20, 1988 -.
Densities (SE) of Seabirds by Species and Groups
Observed in Slope and Shelf-Edge Haters, and the Number
of 15-min Transects Conducted Aboard the Deepwater
Dumpsite-106, September 9 through 20, 1988. .
10
D-3
-------
INTRODUCTION
The Environmental Protection Agency (EPA) is regulating the ocean
disposal of sewage sludge at the 106-Mile Site. These regulatory activities
included the preparation and implementation of a monitoring program for the
site. The acquisition of physical, chemical, and biological data on the water
column and sediments will be used to assess farfield and nearfield fate and
short-term effects of ocean disposal of sewage sludge at the 106-Mile Site. .
These data will include measurements for the following parameters:
1. Water quality parameters (temperature, depth, dissolved oxygen,
transmissometry, salinity, total suspended solids) used to
characterize the water mass.
2. Trace metals (Al, Cu, Fe, Pb, Ag, Zn) in the "water column
" (dissolved and particulate) and sediments. These selected
metals are suggested as important sewage sludge tracers.
3. Organic compounds (PAHs, PCBs) in the water column (dissolved
and particulate) and sediments. These selected compounds are
of specific interest as sewage sludge tracers and pollutants..
4. Microbiology (Clostridium perfrinqens, enterococci, coliforms,
and antibiotic-resistant bacteria) of the water column and
sediments. These organisms are valuable indicators of sewage
as well as other sources of pollution.
Because of the concern for the impact of ocean dumping and disposal of
sewage sludge (DS-106) on endangered species of whales and turtles and in
response to requirements of the Endangered Species Act (ESA), the presence of
these species in the above-mentioned study site was investigated. During the
cruise, a qualified observer of endangered marine species monitored the
presence of whale and turtle populations at and near DS-106.
The objectives of the marine mammal and turtle observer were as follows:
1. To compare the seasonal distribution and abundance (sightings
per unit-effort) of marine mammals and turtles, and densities
(individuals per unit area) of seabirds in the areas
potentially impacted by activities at the DS-106. .
2. To determine behavior and directional movements of cetaceans
relative to the areas impacted by the activities within the
DS-106. •
1
D-4
-------
3. To determine the distribution and abundance of cetaceans and
turtles'in the waters of the DS-106.
In addition, data on the distribution and abundance of seabirds will be
collected at the same time as data on marine mammals and turtles (see Methods).
This report summarizes the marine mammal, seabird, and turtle observations
made by Bert Nickerson, Manomet Bird Observatory, Marine Mammal and Seabird
Studies, aboard the OSV Peter W. Anderson during September 9 through 20, 1988^
i •) . . •
Study Area
The 106-Mile Site is located south of Hudson Canyon over the continental
slope and rise (Figure 1). It is a rectangular area, 37 x 43 km, bounded by
38°40'N, 39°00'N, 72°00'W, and 72°30'W. A description of the physical
characteristics of the dumpsite has been provided (NOAA, 1977). The-physical
oceanographic environment in the site is complex. However, Gulf Stream
currents, warm-core eddies, and seasonal circulation features found in these
waters have been used to delimit a potential area of influence (PAI) from
dumping activities (data reported in Pearce et al., 1983).
METHODS
Sampling Technique
The sampling methods have been designed to allow one observer to collect
information on cetaceans, turtles, and seabirds simultaneously (Powers et al.,
1980). Observations are recorded continuously along a predetermined cruise
path in 15-min periods where each period represents a transect (following Payne
et al., 1984). As a result, the duration of each observation period is
constant, but the linear distance surveyed within each 15-min period depends
upon speed of the -vessel. .
The data are recorded as two major record types—location/environmental
and species/behavior. Both record types are recorded for each 15-min
observation period and are linked by a unique cruise and observation number.
Location/environmental data include the following parameters: latitude-
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NAUTICAL ••*«.<»
o 10 :o JO «o so J
- NEW JERSEY ..
(06 MILE SITE
NORTH
ATLANTIC
INCINERATION
SITE
DELAWARE
ATLANTIC
OCEAN
71'
FIGURE 1. LOCATIONS OF THE 106-MILE SITE AND THE
NORTH ATLANTIC INCINERATION SITE
3
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longitude (deg-min), date, time (yr-mo-day-hr-min), elapsed time (min), vessel
speed (kn) and course (deg N), water depth (m) and temperature deg C),
visibility, and wind direction (deg N) and speed (kn). Species/behavior data
include the following information: species group (mammal, bird, turtle),
species identification, numbers seen, age, color phase (bird only), distance
and angle to sightings (mammals and turtles only), animal heading, animal
association, and behavior noted (see Miller et al., 1980).
The areas surveyed during this cruise were stratified and combined into
subregions based on bottom depth (following the research procedure described by
Grosslein (1969) for the shelf regions north of Cape Hatteras). The location
of each 15-min transect (latitude-longitude) and the location and number of
marine mammals, turtles, and seabirds observed were recorded and assigned to
1 '" ,,!,| i1 "!,' , • .,]»
appropriate subregions to facilitate direct spatial comparisons between
sightings and the study area of special concern. '
Analysis of Census Data
Estimates of.cetacean and turtle abundance (the number of individuals
observed/linear km) were based on the number of cetacean sightings per
transect. Confidence intervals about the abundance estimate are the product of
the standard error of the mean, the appropriate student-t level of confidence
(P<0.05), expanded by the area within the study site.
Payne et al. (1984) found that sightings of marine mammals and turtles
decreased significantly when wind speeds were greater than 17 mph. Therefore,
only census data collected when wind speed was less than 17 mph were examined
in this report.
Estimates of seabird density (birds/km2) were derived from a strip
transect procedure (Powers 1982, 1983). The observer counts all birds on one
side of the ship out to 300 m and forward of mid-ship to the projected end of
the transect. The width of the strip sampled was determined with a hand-held
fixed-interval rangefinder (Heinemann, 1981). A ship-following bird that
passed through the strip for the first timie was counted, but that bird in all
transects thereafter was considered a recount. Recounts were tallied
separately and were not included in the density estimates. This strip-census
method does not eliminate the problem of ship attraction (which varies
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according to cruise objectives) or chronic ship-following (which varies fay bird
species), but it does minimize its inflationary effect on density estimates
(Powers, 1982). Differences in the ability of observers to count birds is the
principal source of variability in any estimate of bird density at sea (Powers,
1982).
Estimates of seabird density were calculated by dividing bird counts from
the sampling strip by the area sampled for each transect. Area sampled (A) per
transect was calculated as follows:
speed (nm/h) x 15 min x 1852 m x 300 n x 1 fan
60 min/h 1 nm 1 x 106
RESULTS AND DISCUSSION
Cetaceans
A total of lie cetaceans (16 sightings) representing 6 species were
observed between September 9 through 20, 1988 (Table 1) in shelf-edge and slope
waters near the 106-Mile Site. Two species of cetacean, the pilot whale
(Globicephala melaena) and the fin whale (Balaenoptera physalus), were observed
in shelf-edge waters (Table 2, Figure 2). However, these species were not
observed in slope waters during the survey. Three other species on non-
endangered dolphins were observed within the boundaries of the site. These
were the bottlenosed dolphin (Tursiops truncatus). the saddleback or common
dolphin (Delphinus delphis). and the grampus or Risso's dolphin (Grampus
qriseus) (Figure 2). The sperm whale (Physeter macrocephalus). an endangered
species, was also observed within the boundaries of the site at 38°47'N,
72°0rw on September 11..
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TABLE 1. LIST OF ALL MARINE MAMMAL OBSERVATIONS IN SLOPE AND SHELF-
EDGE HATERS DURING THE BASELINE SURVEY TO THE DEEPWATER
DUMPSITE 106, SEPTEMBER 9 THROUGH 20, 1988
Species 1
Pilot whale
(Globicephala melaena)
Bottlenosed dolphin
(Tursiops truncatus)
Grampus or Risso's dolphin
(Grampus griseus)
Common or saddleback dolphin
(Delphinus -del phis)
Sperm whale
(Physeter macrocephalus)
Fin whale
(Balaenoptera physalus)
Unidentified dolphins
(Delphinidae spp.)
Unidentified whale
Number
5(1)
5(1)
20(1)
10(1)
2(1)
5(1)
- 2(1)
KD
2(1)
2(1)
2(1)
3(1)
35(1)
KD
20(1)
KD
Location
39°46
39
39
39
38
38
38
38
38
38
38
38
' 38
38
38
39
o
o
0
o
o
o
o
0
o
o
o
o
o
o
0
07
02
00
50
46
47
44
44
44
44
52
59
49
50
12
'N,
'N,
'N,
'N,
'N,
'N,
'N,
'N,
'N,
'N,
'N,
'N,
'N,
|Nr
'N,
71
72
72
72
72
72
72
73
73
73
73
72
72
71
72
72
°37
°03
°04
°09
o
01
°25
0
0
0
o
o
o
o
o
o
o
01
09
05
05
01
25
05
55
01
03
'W
'W
'W
'W
'W
'W
'W
'W
'W
'W
'W
'W
'W
'W
'W
'W
Date
09
09
16
18
18
11
11
11
11
11
11
11
16
18
18
17
Sep
W W f*
Sep
Sep.
Sep
Sep
Sep .
Sep
Sep
Sep
Sep
Sep
Sep
Sep
Sep
Sep
Sep
iThis table includes all sightings on the cruise. Sightings which occurred
at wind speeds greater than 17 kn, or outside the 15-min transect periods.
(therefore non-quantitative), are not reflected in the relative abundances
of cetaceans presented in Table 2, but are presented in Table 1.
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TABLE 2. RELATIVE ABUNDANCE (SE) OF CETACEANS BY SPECIES OBSERVED
IN SLOPE AND SHELF-EDGE HATERS, AND THE NUMBER OF 15-MIN
TRANSECTS CONDUCTED ABOARD THE OSV Peter W. Anderson
DURING THE BASELINE SURVEY TO DEEPWATER DUMPSITE-106.
SEPTEMBER 9 THROUGH 20, 1988
Species
Relative Abundance (SE)
5 lope
(N=69)
Shelf-Edge
Pilot whale
Bottlenosed dolphin
Saddleback dolphin
Unidentified dolphin spp.
Total Dolphin sp.
0.271 (0.159)
0.024 (0.024)
0.017 (0.017)
0.312 (0.162)
0.250 (0.250)
0.250 (0.250)
Fin whale
Sperm whale
Total Large Whale spp.
0.159 (0.074)
0.029 (0.029)
0.029 (0.029) 0.159 (0.074)
7
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• I I ' • • ..
0 10 ZO JO 40 30 ',
4 I
40
39
NORTH
ATLANTIC
INCINERATION
SITE
33
DOLPHINS
WHALES
ATLANTIC
OCEAN
37
75'
74
73
72
71'
FIGURE 2. LOCATION OF CETACEAN SIGHTINGS OBSERVED ABOARD
THE OSV Peter H. Anderson. SEPTEMBER 9 THROUGH
20, 1988
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Marine Turtles
There were no sightings of marine turtles observed during this survey.
Seabirds
Wilson's storm-petrels, Oceanites oceanicus, were the only species of
seabird observed in shelf-edge waters during this survey (Table 3). Wilson's
storm-petrels accounted for 75 percent of the total seabird density in slope
waters during this survey. The largest aggregation of storm-petrels occurred
in slope waters at 39°irN, 72°09'W.
Three species of shearwaters, the Manx shearwater (Puffinus). Cory's
shearwater (Calonectris diomedea). and Audubon's shearwaters (Puffinus
Iherminieri) were also recorded throughout slope waters; The Audubon's
shearwater was more abundant than the other two species by an order of
magnitude (Table 3).
Cetacean Sightings Relative to the 106-Mile Site
This is the third consecutive fall or spring survey within the boundaries
of the 106-Mile Site where an endangered species (either sperm whales or fin
whales) were observed. Although major concentrations of sperm whales are i
generally considered north and east of the site during late summer and fall, it
is apparent that a portion of this population occurs in the slope waters of the
site from spring through fall.
It is likely that fin whales occur in this location throughout the year.
The north-south movements of this species occur along shelf-edge and slope
waters adjacent to the dumpsite.
LITERATURE CITED
Heinemann, D. 1981. A rangefinder for pelagic bird censusinq. J. Wildl.
Manage. 45:489-493.
Miller, D.S., P.M. Payne,a nd K.D. Powers. 1980. Marine Observer Manual, App.
B - A Marine Observer Training Program. Nat. Mar. Fish. Service,
Northeast Fish. Center Contr. NA-80-FA-D-0004. 147 pp.
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TABLE 3. DENSITIES (SE) OF SEABIRDS BY SPECIES AND SPECIES GROUPS
OBSERVED IN SLOPE AND SHELF-EDGE WATERS, AND THE NUMBER
OF 15-MIN TRANSECTS CONDUCTED ABOARD THE OSV Peter W. Anderson.
DURING THE BASELINE SURVEY TO DEEPWATER DUMPSITE-106,
SEPTEMBER 9 THROUGH 20, 1988
Species
Density (SE)
Slope
(N=69)
Shelf Edge
Manx shearwater
(Puffinus puffinus)
Cory's shearwater
(Calonectris diomedea)
Audubon's shearwater
(Puffinus Ihermim'eri
Total Shearwater spp.
Herring gull
(Larus arqentatus)
Ring-billed gull
(Larus delawarensis)
Total Gull spp.
Wilson's storm-petrel
(Oceanites oceam'cus)
Common tern
(Sterna hirundo)
Pomarine jaeger
(Stercorarius pomarinus)
0.044 (0.035)
0.026. (0.0i9)
0.216 (0.125)
0.286 (0.142)
0.010 (0.010)
0.009 (0.009)
* •?
0.019 (0.002)
1.151 (0.802)
0.065 (0.041)
0.010 (0.010)
1.630 (0.976)
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Payne, P.M., L.A. Selzer, and A.R. Knowlton. 1984. Distribution and dens'ftv'
of cetaceans, marine turtles and seabirds in the shelf waters of the
northeastern United States, June 1981 - .December 1983, based on shipboard
observations. NMFS/NEFC Contract NA-.81-FA-C-00023. 246 p.
Powers, K.D., P.M. Payne, and D.5. Miller. 1980. A Marine Mammal Observer
I^iS1?? nrn2nam* Fina1 Report to NOAA/NMFS/NEFC, Contract No.
NA-80-FA-D-0004, Woods Hole, MA. 73 pp.
Powers, K.D. 1982. A comparison of two methods of counting birds at sea J
Field Ormth. 53:209-222.
Powers, K.D. 1983. Pelagic Distribution of Marine Birds off the Northeastern
United States. NOAA Tech. Mem. NMFS-F/NEC-27. 199 pp.
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