FINAL REPORT
CONTAMINANT BODY BURDENS IN
MESOPELAGIC FISH (XYCTOPBIDAE)
COLLECTED NEAR THE 106-MILE SITE
September 30, 1989
U.S. ENVIRONMENTAL PROTECTION AGENCY
Office of Marine and Estuarine Protection
Washington, DC
Prepared Under Contract No. 68-C8-0105
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ACKNOWLEDGEMENTS
This is to acknowledge the participation of the following persons from
Battelle Ocean Sciences in the preparation of this report: D. Shea, C.D.
Hunt, N.S. Young, W.G. Steinhauer, G.S. Durell, and C.S. Peven.
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TABLE OF CONTENTS
Page
1.0 INTRODUCTION 1
1.1 Background 1
1.2 Objectives and Scope of Work 2
1.3 Selection of Organic Contaminants ...-. 3
1.4 Selection of Indicator Organism 5
2.0 SURVEY DESCRIPTION 7
2.1 Station Locations... 7
2.2 Sampling Methods 7
3.0 ANALYTICAL METHODS 10
3.1 Sample Preparation 11
3.2 Instrumental Analysis 12
4.0 RESULTS AND DISCUSSION 13
4.1 Polychlorinated Biphenyls (PCB) 16
4.2 Pesticides 25
4.3 Polynuclear Aromatic Hydrocarbons (PAH) 27
4.4 Linear Alkyl Benzenes (LAB) 27
4.5 Physical Oceanographic Data 29
5.0 CONCLUDING REMARKS 33
5.1 Summary and Conclusions 33
5.2 Recommendations 36
6.0 REFERENCES 37
APPENDIX A. Data Quality Requirements and Quality Control Results A-l
APPENDIX B. Trawl Location Logs B-l
APPENDIX C. Hydrographic Profiles C-l
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LIST OF TABLES
Page
Table 1 MYCTOPHID SAMPLES COLLECTED ON SURVEY 14
Table 2 MYCTOPHID SAMPLES ANALYZED FOR
ORGANIC CONTAMINANTS 15
Table 3 RESULTS OF PCB BODY BURDEN ANALYSES 17
Table 4 MEAN PCB AND PESTICIDE CONCENTRATIONS
IN MYCTOPHID NEAR THE 106-MILE SITE 19
Table 5 RESULTS OF PESTICIDE BODY BURDEN ANALYSES 26
Table 6 RESULTS OF PAH AND LAB BODY BURDEN ANALYSES 28
LIST OF FIGURES
Page
Figure 1 DRAWING OF MYCTOPHIDAE MYCTOPHUM 6
Figure 2 LOCATION OF THE 106-MILE SITE AND SAMPLING STATIONS
FOR JUNE NOAA/EPA MYCTOPHID SURVEY 8
Figure 3 DISTRIBUTION OF PCB IN MYCTOPHID
COLLECTED AT THE 106-MILE SITE 21
Figure 4 DISTRIBUTION OF PCB IN MYCTOPHID COLLECTED
100 MILES S.W. OF THE 106-MILE SITE 22
Figure 5 DISTRIBUTION OF PCB IN MYCTOPHID
COLLECTED IN THE SARGASSO SEA 23
Figure 6 DISTRIBUTION OF PCB IN MYCTOPHID COLLECTED
80 MILES N.E. OF THE 106-MILE SITE 24
Figure 7 SATELLITE THERMAL IMAGERY DATA FROM JUNE 11, 1989... 30
Figure 8 CURRENT VECTORS FOR 25 AND 100 METERS
AT THE 106-MILE SITE 32
Figure 9 PCB AND PESTICIDE DIAGNOSTICS RATIOS IN MYCTOPHID: TOTAL
PCB (PCB), TOTAL PESTICIDE (PEST), AND TOTAL DDT (DDT) 35
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1.0 INTRODUCTION
1.1 BACKGROUND
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. A monitoring program has been
designed for the 106-Mile Deepwater Municipal Sludge Site (106-Mile Site),
which was designated in 1984 for disposal of municipal sludges ( EPA ,
1992a). The program is being implemented according to a tiered approach
( EPA 1992b), whereby data generated in one tier are used in making
management decisions about continued site designation, awarding of dumping
permits, and the design and implementation of future surveys.
In,March 1989, EPA, the National Oceanic and Atmospheric Administration
(NOAA), and the U.S. Coast .Guard jointly sponsored a workshop to address
management issues on sewage sludge dumping at the 106-Mile Site (EPA, in
press). Many recommendations were made (EPA, 1989), including a priority
placed on assessing possible impacts on indigenous fish populations at the
site. Criteria for selection of the fish species included residency at and
near the 106-Mile Site and residence in the near surface water (epipelagic
zone). The latter criterion is important because contaminants are
concentrated on the finer-grained particles in the sewage sludge (Boehm,
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1983), and these particles appear to have a long residence time in the
epipelagic zone ( EPA , 1992c). This could result in long-term exposure
of indigenous organisms to contaminants in the sludge. The workshop also
strongly recommended enhanced cooperation among the government agencies
interested in sewage-sludge disposal at the 106-Mile Site.
Prior to the workshop, NOAA planned a June 1989 survey of the 106-Mile Site
and areas up to 100 miles north, south, and east of the 106-Mile Site to
collect and analyze mesopelagic fish for mercury content. In part because
of the workshop recommendations, NOAA increased the number of metals to be
analyzed from 1 to 13. NOAA also offered EPA the opportunity to
participate in this survey, and EPA responded by funding the analysis of
organic contaminants in fish collected in the survey. This analysis was
completed by Battelle Ocean Sciences (Battelle) under Work Assignment 38
(WA 38). NOAA concurrently performed metal analysis of replicated fish
collected in the survey.
1.2 OBJECTIVES AND SCOPE OF WORK
Mesopelagic fish indigenous to the 106-Mile Site were analyzed for organic
contaminants to provide chemical data for an initial assessment of the
impact of sewage-sludge dumping on fish residing at and near the 106-Mile
Site. Although not originally part of the 106-Mile Site Implementation
Plan ( EPA 1992b), results from this survey can be used to support the
evaluation of long-term effects (Tier 4 of the monitoring program). This
is made possible by comparing contaminant body burdens in fish resident at
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the 106-Mile Site with those collected upstream and downstream from the
site and with those collected in the Sargasso Sea (control site). Site ,
selection and field operations were performed by NOAA aboard the R/V
Delaware II. Battelle provided assistance in the collection of fish at the
106-Mile Site and conducted whole-body analyses of organic contaminants.
This report provides a description of the NOAA survey, the results of the
organic contaminant analysis, and an interpretive discussion of these data
to evaluate the impact of sewage sludge dumping at the 106-Mile Site on
indigenous fish. Additional tasks provided under WA38 included assistance
on a second NOAA survey (Atlantis II - Alvin) in September 1989 to collect
benthic and other fish and shellfish species at the 106-Mile Site and a
similar survey in September 1989 conducted by the National Undersea !
Research Program (NURP) at the University of Connecticut. Battelle has
received and archived 15 fish tissue samples collected in the Alvin survey
and 15 sediment samples collected in the NURP survey. Additional sampling
in the NURP survey has been delayed until May or June of 1990 because of
structural problems with the submersible sphere. These other surveys are
not discussed further in this report.
1.3 SELECTION OF ORGANIC CONTAMINANTS
Several studies have been performed to characterize the chemical
composition of sewage sludges originating from the Metropolitan New York
area and dumped at the 106-Mile Site (Boehm, 1983; MacLeod, 1981;
Ecological Analysts, 1983;). Both organic and inorganic chemical
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contaminants are enriched in sewage sludge, but their concentrations can be
highly variable both within and between particular sludge sources. There
are considerably more data on the levels of inorganic contaminants (e.g.,
metals) than there are for individual organic compounds. Data from recent
sludge-characterization studies (Boehm, 1983; MacLeod, 1981; Ecological
Analysts, 1983; Eganhouse et al., 1988) indicate that polychlorinated
biphenyls (PCB), chlorinated pesticides including DDT and its metabolites,
polynuclear aromatic hydrocarbons (PAH), and linear alkyl benzenes (LAB)
are all enriched in sewage sludge (relative to background particles in the
ocean). These contaminants also can persist for many years in the marine
environment, and, because of their lipophilicity, can accumulate in the
lipid tissues of fish that reside in and near the 106-Mile Site.
In addition, PCB, PAH, and pesticides are potentially toxic, mutagenic,
carcinogenic, and/or teratogenic to marine organisms and, consequently,
pose a significant ecological threat at high exposure levels. The body
burdens of PCB, PAH, and pesticides are potential chemical indicators of
the impact of sewage-sludge dumping on resident fish. LAB do not
themselves pose a significant ecological problem, but they have been used
as markers of the hydrocarbon component of sewage sludge and other domestic
wastes (Eganhouse et al., 1983, 1988).
Although coprostanol is a more common tracer for sewage sludge and has been
measured in *ater and particulate samples in previous surveys at the 106-
Mile Site, it was not measured in this study because the high level of
other sterols in the fish was expected to interfere with the analysis.
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Trace-metal contaminants will be measured by NOAA in replicated fish
samples and are not discussed in this report.
1.4 SELECTION OF INDICATOR ORGANISM
To evaluate the biological effects of sewage-sludge disposal at the 106-
Mile Site, an appropriate indicator organism is required. The criteria for
selecting an indicator organism in this study were
(1) Full- or part-time residency in epipelagic zone at the 106-Mile Site
and Sargasso Sea (control site),
(2) Sufficient biomass for analysis of metals and organic contaminants,
(3) Restricted horizontal migration.
Myctophidae is one of the most abundant families of fish in the Mesopelagic
zone. Commonly called lanternfish because of the rows of photophores on .
the body and head, they live primarily between 100 and 1000 m. A drawing
of a myctophid (Myctophum) is presented in Figure 1. Myctophids do not
migrate horizontally to any great extent, although they will move with the
surrounding water mass. Myctophids do migrate vertically each night to the
epipelagic zone, where they feed on zooplankton and fish. Thus, as part-
time residents above the pycnocline, the myctophids meet the three
selection criteria given above.
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2.0 SURVEY DESCRIPTION
2.1 STATION LOCATIONS
During June 6-18, 1989 NOAA conducted a survey of the 106-Mile Site, aboard
the R/V Delaware II, to collect mesopelagic fish at four stations:
Station 1 - 106-Mile Site
Station 2 - 100 miles southwest of the 106-Mile Site j
Station 3 - Sargasso Sea
Station 4-80 miles northeast of the 106-Mile Site
The location of each station (Figure 2) was determined by using the LORAN-C
electronic navigation system aboard the R/V Delaware II. Each tow's start
and end points and duration, as well as tow depth, bottom depth, mean wire
out, and the approximate number of myctophids per sample were recorded in
Trawl Location Logs, which are presented in Appendix B.
2.2 SAMPLING METHODS
An Isaacs-Kid Mid-Water Trawl was deployed for sample collection. The net
and cod-end catch bag of the trawl were constructed of polypropylene mesh.
The cod-end catch bag was secured with rope and cable ties. The trawl was
towed for approximately 1 hour at each station. The depth of the tow was
dictated by the time of day samples were being collected. Stations 1 and 2
were sampled-at nighttime, with the tows conducted primarily at <50 m
depths. Stations 3 and 4 were sampled at daytime, with tows conducted at
depths of 400 to 800 m.. . • '
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76e 75C
74
73°
106-MILE SITE
(STATION 1)
35 °N
70 °W
LONGITUDE
FIGURE 2. LOCATION OF THE 106-MILE SITE AND SAMPLING STATIONS FOR JUNE
NOAA/EPA MYCTOPHID SURVEY.
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Upon retrieval of the trawl, the cod end was hoisted via the boom directly
from the water to a stainless steel collection tray that had been prewashed
with soap and water, distilled water, methanol, and methylene chloride.
The contents of the trawl were emptied onto the collection tray where the
dominant myctophid and/or other mesopelagic species were sorted,
identified, and split for organic and trace metal subsamples.
The subsamples were transferred to fiberglass trays lined with solvent-
rinsed foil and were taken into the laboratory .for processing. Teflon
forceps were used to transfer the subsamples from the fiberglass tray into
prewashed (as described above) 500-mL Teflon jars. Each sample jar was
appropriately labeled from the myctophid sampling log and the label was
secured with clear plastic tape. Each sample-jar lid was further secured
with tape to ensure sample integrity. The species and the number of
animals were recorded in the myctophid sampling log. Samples were
maintained at - 20°C in the vessel's freezer until June 19, 1989, at which
time samples for organic analyses were transferred by truck to Battelle and
stored at - 20°C. Samples for metal analyses were transferred to the NOAA,
National Marine Fisheries Service (NMFS) Sandy Hook, NJ laboratory (Mr.
Vincent Zdanowicz).
At each of the four stations, an attempt was made to collect three
replications, each containing four myctophidae species. At all four
stations, multiple tows were required to attain sufficient biomass. Each
organic sample replication corresponds to a unique tow. However, time
constraints and a lack of species diversity and biomass precluded the
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collection of four myctophidae species per station as originally proposed
in the Work Plan.
The Isaacs-Kid Mid-Water Trawl required deployment and retrieval at an
angle. On one occasion this caused the side arms of the depressor foot to
bend, rendering the trawl inoperable. The trawl type and the tow duration
(1 hour) often caused severe trauma rendering many of the fish
unidentifiable as to genus and species. These samples were identified as
Myctophidae Composites. The most severely traumatized samples were not
used for organic analysis.
3.0 ANALYTICAL METHODS
Tissue samples were prepared and analyzed for PAH, LAB, and pesticide/PCB
analysis following methods established for the NOAA National Status and
Trends Mussel Watch Program (Battelle, 1988 ), with minor modifications
made to those methods for the analysis of LAB. Additional modifications to
the sample-preparation procedures were necessary because of the unusually
high lipid content of myctophids. The excess lipid was removed with an
additional cleanup procedure to minimize potential interferences in the
instrumental analysis. A brief description of the sample preparation and
analyses, including all modifications to the Mussel Watch Program, is given
below.
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3.1 SAMPLE PREPARATION
A 10 - 15 g aliquot of fish tissue was homogenized with a Tekmar Inc.
Tissumizer. The homogenate was spiked with the appropriate PAH, LAB, and
pesticide/PCB quantisation internal standards. The compound
dibromooctafluororobiphenyl (DBOFB) was used for the pesticide/PCB internal
standard, a mixture of d8-naphthalene, dlO-acenaphthene, d!2-perylene, and
d!2-benzo[a]pyrene (except one batch, 1A) was used for the PAH internal
standard, and the compound 1-phenyl nonane was used for the LAB internal
standard.
The spiked homogenate was mixed with 40 g sodium sulfate, and extracted for
5 minutes with methylene chloride. The mixture was centrifuged, the
methylene chloride was decanted and reserved, and the extraction was
procedure repeated twice more. The combined solvent extract was passed
through an alumina column for lipid removal. The extract was concentrated
to approximately 1 ml, using Kuderna-Danish techniques. Additional cleanup
was necessary because of the high lipid content of the fish and was
performed by using a high performance liquid chromatographic (HPLC) gel
permeation technique (Krahn et al., 1988). Extracts were diluted to 4 mL,
and 1-mL fractions were separately loaded onto a Phenomonex 100 A gel
permeation column and isocraticalTy eluted with methylene chloride. The
eluted fractions were combined and the volume reduced by gentle nitrogen
gas evaporation to approximately 500 (tL.
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Just prior to instrumental analysis, the samples were spiked with PAH/LAB
and pesticide/PCB recovery internal standards, which are used to measure
the recovery of the quantisation internal standards. The compound
tetrachloro-m-xylene (TCMX) was used as the recovery internal standard for
pesticide/PCB analysis, and the compound dl2-chrysene was used as the
PAH/LAB recovery internal standard.
Sample dry weight was determined by removing a 1 - 5g aliquot of macerated
tissue and weighing after drying overnight at 105°C. Sample percent
moisture values ranged from 70 - 80 %.
3.2 INSTRUMENTAL ANALYSIS
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 E
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Tissue extracts were analyzed by capillary gas chromatography with electron
capture detection (GC/ECD) for pesticide/PCB content. Any pesticide or PCB
identified in the samples were quantified by using the method of internal
standards. Results are reported in ng/g of tissue, on a dry-weight basis.
Data quality requirements and objectives and the results of quality control
sample analyses are given in the Appendix A.
4.0 RESULTS AND DISCUSSION
The mesopelagic species collected during the NOAA June 1989 survey are
listed in Table 1. Although, 35 samples were obtained for organic
analysis, available funds allowed the analyses of only 12 samples. The
criteria used to select samples for analysis were
(1) Station and species commonality with NOAA selections
(2) Adequate spatial coverage and control samples
(3) Replicated samples (where available).
Based on these criteria, 14 samples were initially identified for analysis.
However, upon close inspection of the samples, it was found that the second
replication for myctophidae composite for Stations 2 and 4 was highly
traumatized as a result of the trawl and only unidentifiable tissue pieces
remained. Organic analysis was not performed on the two,highly traumatized
samples because of the loss of sample integrity. All other samples
remained sufficiently intact and whole-body organic analysis was performed.
A list of the 12 samples analyzed is given in Table 2. Results of the
13.
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TABLE 2. MYCTOPHID SAMPLES ANALYZED FOR ORGANIC CONTAMINANTS.
Species
Identification
Hygophum hygomi
Benthosema glacials
Benthosema glaciale
Myctophidae Composite
Myctophidae Composite
Myctophidae Composite
Hygophum hygomi
Hygophum hygomi
Myctophidae Composite
Benthosema glaciale
Benthosema glaciale
Myctophidae Composite
Station-
Replicate-
Species Codea
1-1-HH
1-2-BG
1-3-BG
l-3-MC(l)
l-3-MC(2)
2-1-MC
2-2-HH
2-3-HH
3-1,4-MC
4-1-BG
4-2-BG
4-2-MC
Depth
(m)
600
362
29
29
29
step
40
35
step
600
800 '
800
Date
(M/D/Y)
6/13/89
6/13/89
6/13/89
6/13/89
6/13/89
6/12/89
6/12/89
6/12/89
6/12/89
6/14/89
6/14/89
6/14/89
Sample
Identification
AAL092A2 "
AAL093A2 \
AAL094A2
AAL094A4
AAL094A5
AAL088A2
AAL089A2
AAL090A2
AAL091A2
AAL095A2
AAL096A2
AAL096A4
a) Code definition: Station number-Replicate number-First letter of genus
and species. Number in parenthesis indicates replication within a
single trawl.
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analyses for organic contaminants in the 12 myctophid samples collected
during the June 1989 survey are presented and discussed below.
4.1 POLYCHLORINATED BIPHENYLS (PCB)
Worldwide usage of PCB has decreased dramatically in recent years, but the
input of PCB into the marine environment continues because of its
resistance to chemical and biological degradation and its numerous
transport mechanisms, including ocean dumping of sewage sludge. Also,
marine organisms, such as myctophids, are slow to metabolize PCB and they
can accumulate these contaminants in lipid tissues. Thus, PCB body burdens
in myctophids can provide a useful indicator of PCB exposure.
The results of 12 analyses for PCB in myctophids are given in Table 3. The
data are for individual congeners, level of chlorination, and total PCB.
The individual isomer determinations and level of chlorinatipn allow
molecular distributions of PCB to be plotted for each sample.
Compositional variations between the samples can reveal possible sources of
PCB at each sampling site and, therefore, are useful in assessing the
impact of a particular source (e.g., sewage sludge) at each site.
Comparison of these data to Aroclor formulations is presented below, but is
not necessarily justified for fish because of the probability of selective
uptake and metabolism of PCB congeners (favoring the accumulation of highly
chlorinated PCB). In addition, the sample stations are located far from
their original source, allowing weathering and partitioning processes to
become a significant factor in the PCB distributions. Although laboratory
experiments on the uptake and metabolism of PCB in myctophids have not been
16
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reported, it is likely that these processes are consistent within the
myctophidae family. Thus, the relative abundance of PCB congeners may not
be indicative of exposure to particular Aroclors, but differences in the
distribution patterns between stations are indicative of different sources
of PCB.
The mean total PCB concentrations at each station are listed in Table 4.
The intrastation variability was very low at all sites, and the range of
mean values between stations was small. There is no statistical difference
between the mean total PCB concentrations at Stations 1 and 2. However,
Station 4 (upstream), had PCB body burdens significantly higher (a factor
of 2) than those of Stations 1 and 2, with PCB concentrations at Station 3
falling within this range. This is particularly interesting because
Station 4 was chosen to represent a possible "reference" site that is not
impacted by sewage-sludge dumping at the 106-Mile Site.
The mean PCB and pesticide body burdens for 21 mesopelagic fish collected
from 20 different sites (all east of latitude 50°W) in the North Atlantic
in 1972 (Harvey et al. 1974) are listed in Table 4. These data represent
several different species, including Benthosema glaciale, Myctophum
punctatum, Protomyctophum articulum, Ceratoscopelus warmingi,
Ceratoscopelus maderenisis, and Hygophum hygomi. Comparison of these
earlier data with those reported here indicates that there has been no
statistically significant change in the PCB body burdens over the last 17
years, assuming that the fish collected near the 106-Mile Site can be
compared to those collected throughout the North Atlantic. In addition, it
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ABLE 4. MEAN PCB AND PESTICIDE CONCENTRATIONS (DRY WEIGHT) IN MYCTOPHID COLLECTED NEAR
THE 106-MILE SITE.1
CB (Total)
esticide (Total)
iDT (Total)3
Station 1
(ng/g)
26.3±8.6
50.5*18.5
26.1*11.2
Station 2
(ng/g)
27.1*6.3
31.1*3.3
16.4*3.2
Station 3
(ng/g)
40.6
12.5
8.7
Station 4
(ng/g)
60.7*1.2
166±32
74.7±9.6
Atlantic2
(ng/g)
57*49 .
NA •
8.0±6.3
Mean valve plus or minus standard deviation. ^ ,
Data from Harvey et al,. (1974). NA: Data not 'a,van!alb-TV;
-DBE-,<:p,,p' -ODD., and p.-p'-DDT only. ._:•., , .
^
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19
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is apparent from these data that mesopelagic fish residing at the 106-Mile
Site are not accumulating PCB to any greater extent than those fish from
the other stations or elsewhere in the Atlantic. In all samples analyzed
from this survey, the total PCB concentrations were low relative to PCB
levels found in coastal fish near urban harbors, 0.5 to 300 ug/g (Weaver,
1984), and the current FDA action limit, 2 ug/g.
The level of chlorination in each sample is plotted in Figures 3 - 6 as a
function of the percentage of total PCB. The tetrachlorobiphenyl dominates
the molecular distribution of samples collected at the 106-Mile Site
(Figure 3), but there is a significant contribution from the penta-, hexa-,
and hepta-chlorobiphenyls. This corresponds to a mixture of Aroclors, with
1248 and 1254 containing the tetra- and penta-chlorobiphenyls and Aroclor
1260 and possibly 1262 contributing the hexa- and hepta-chlorobiphenyls.
Aroclors 1254 and 1260 are the most abundant PCB formulations in the sewage
sludge dumped at the 106-Mile Site (Ecological Analysts, 1983). A more
distinct bimodal distribution is found for samples collected at Station 2,
100 miles southwest (downstream) of the 106-Mile Site (Figure 4), but it is
shifted toward higher chlorination (Figure 4). This indicates possible
enrichment of Aroclor 1260 in these samples. The distribution of PCB in
the Sargasso Sea sample (Station 3) is enriched in the hepta- and octa-
chlorobiphenyls as shown in Figure 5. This pattern is unique among the
samples collected in this survey and indicates exposure of myctophids to
only highly chlorinated PCB (e.g., Aroclor 1262). At Station 4, 80 miles
northeast (upstream) of the 106-Mile Site, a bimodal distribution exists
20
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(Figure 6); the pattern is similar to that found for Station 1. Station 4
also contained the highest absolute concentrations of PCB (Table 4).
4.2 PESTICIDES
The results of 12 analyses for pesticides in myctophids are given in Table
5. The majority of the values are very low, but pesticides were detected
in all samples and aldrin was the only compound not detected. The mean
total pesticide values for each station are listed in Table 4. Within-
station variability was low, but there are significant differences among
the pesticide body burdens at the stations. The pesticide levels in the
fish from the Sargasso Sea (Station 3) were significantly lower than those
at the other stations. A gradient was found along Stations 1, 2 and 4;
with concentrations decreasing from north to south. The pesticide body
burdens were 4 times higher at the 106-Mile Site (Station 1) than the
Sargasso Sea (Station 3), 2.5 times higher downstream (Station 2), and more
than an order of magnitude higher upstream (Station 4). The enrichment of
pesticides in the tissues of mesopelagic fish upstream from the 106-Mile
Site is consistent with, but more dramatic than, that seen for PCB body
burdens. Harvey et al. (1974) measured total DDT (PPDDE, PPDDD, and PPDDT)
in North Atlantic myctophids (20 different sites) and the mean value is
comparable to that of Station 3 (Table 4).
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4.3 POLYNUCLEAR AROMATIC HYDROCARBONS (PAH)
The PAH body burden data for the myctophids are given in Table 6. Most of
the data are below the detection limit, and all of the measured values are
trace levels. The few elevated naphthalene values are probably the result
of laboratory contamination. These low values are consistent with previous
studies of PAH body burdens in fish tissue. PAH levels in fish tissue are
usually very low or not detectable even in heavily polluted waters because
PAH are easily metabolized by most fish. Assessing the exposure of fish to
PAH would require analysis of the PAH metabolites.
4.4 LINEAR ALKYL BENZENES (LAB)
The LAB are a group of phenyl alkanes having a benzene ring with a straight
alky! chain of between 9 and 15 carbons. LAB are precursors used in the
production of linear alkyl benzenesulphonate surfactants (LAS), which are
common in domestic detergents. Unreacted LAB remain in the detergent
product as impurities; they may also result from desulfonation of LAS.
Eventually LAB can appear in domestic wastes and sewage sludge. Although
the initial concentrations of LAS are higher than those of LAB, LAS are
easily oxidized (both photochemical1y and microbially); therefore they do
not. persist in the environment. Conversely, LAB are more resistent to
oxidation than are LAS and may be preserved in sediments for decades
(Eganhouse et al., 1988). This stability has led to the use of LAB as a
geochronological marker and as a chemical tracer for domestic wastes and
27
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sewage sludge. Although there are several reports of LAB measurements in
sediments and particulate matter, very little work has been reported on
measuring LAB in tissues of organisms that have been exposed to sewage.
Murray et al. (1987) found LAB in a single mussel sample collected near
Port Phillip Bay (Australia) sediments enriched in LAB, and some studies
have been performed on the microbial oxidation of LAB in cultures (Bayona
et al., 1986). This study provides the first field evaluation of LAB as a
chemical indicator of biological exposure to sewage sludge at the 106-Mile
Site.
Results obtained from the LAB body-burden analyses are listed in Table 6,
with essentially all of the data near or below the detection limit.
Extremely low levels of LAB in fish tissue could result from either limited
exposure to sludge particles or rapid metabolism of the.aliphatic chains.
In addition, laboratory and/or field contamination from detergents
(containing high levels of LAB) could introduce measurable LAB to the
sample, and may account for the high n-tetradecyl-benzene values. All of
the LAB compounds were detected in the sample from the Sargasso Sea
(Station 3), giving further indication of contamination.
4.5 PHYSICAL OCEANOGRAPHIC DATA
The satellite thermal- imagery data for June 11, 1989 is shown in Figure 7.
These data were prepared by Margaret Sano of the Marine Climatology
Investigation of the National Marine Fisheries Service. This low-
resolution analysis provides a composite view of the Gulf Stream position,
29
-------
JUNE 11, 1989 NOAA-11 AVHRR IMAGE AND MYCTOPHID TRAWL STATIONS
5 "I-* '8
1530
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f iodRL "7. •"•SATELLITE THERMAL IMAGERY DATA FROM JUNE 11, 1989.
30
-------
the location of the shelf water/slope water front, and the positions of
warm-core and cold-core eddies formed by Gulf Stream meanders. However,
surface warming reduces the thermal contrast between these water masses
during the summer. The data show that during the sampling period Station 3
was in the Sargasso Sea, about 20 miles southeast of the Gulf Stream.
Station 2 was located in slope water, but was very close to the Gulf
Stream. Stations 1 and 4 were located in slope water, over 10 miles north
of the Gulf Stream, these data alone are not sufficient to attempt
correlations between water masses and contaminant body burdens.
Near-surface current velocity and direction at the 106-Mile Site were
monitored with the moored current meters in place at 25 m and 100 m depths.
Vector profiles for the time period 15 May to 18 June,. 1989 are shown in
Figure 8. For the three weeks prior to sampling, current velocities were
moderately weak (<30 cm/s) and the prevailing current direction was toward
the northeast. Around 8 June, 1989 the current direction shifted toward
the south and remained that way throughout the survey. The maximum current
velocity was about 40 cm/s. There is no evidence of water movement (or
contaminant transport) from Station 1 (106-Mile Site) toward Station 4 over
this 1 month period.
Hydrographic profiles of temperature, salinity and sigma-t are given in
Appendix C. '
31
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5.0 CONCLUDING REMARKS
5.1 SUMMARY AND CONCLUSIONS
The objectives of this work assignment were to conduct an initial
assessment of the impact of sewage-sludge disposal on indigenous fish in
the vicinity of the 106-Mile Site and evaluate the feasibility of
monitoring the bioaccumulation of sludge-related contaminants in
mesopelagic fish. Myctophids were collected at four stations: the 106-Mile
Site, 100 miles southwest and 80 miles northeast of the 106-Mile Site, and
the Sargasso Sea.
Contaminant body burdens in these fish provided a good indication of low
level exposure to PCB and pesticides at all four stations, but the data
were not sufficient to determine the source of the contaminants.
Concentrations of almost all PAH and LAB were near or below the detection
limit for all of the samples. Both PAH and LAB are readily metabolized by
fish, so the low levels reported here are not necessarily a result of low
exposure.
Trace levels of PCB and pesticides were found in fish at all stations. The
highest concentrations were found at Station 4, 80 miles northeast of the
106-Mile Site. Very little difference was found in the levels of PCB and
pesticide at Stations 1 and 2 and only small differences were found in the
distribution of PCB in fish at Stations 1, 2, and 4. However, Station 3
exhibited a unique PCB distribution (higher level of chlorination),
•33 .
-------
indicating either a unique source of PCB or the PCB was more weathered.
There were no apparent interspecies differences in the amount or
distribution of PCB and pesticides in myctophids.
To gain more insight into possible PCB and pesticide sources, diagnostic
ratios of total pesticide/total PCB, total DDT/total PCB, total DDT/total
pesticide are plotted in Figure 9. These diagnostic ratios show a clear
similarity between Stations 1 and 4, while Station 3 again exhibits a
unique pattern. Diagnostic ratios for Station 2 fall within this range and
are closest to those of Stations 1 and 4. Pesticide/PCB ratios found in
this study are simialr to those of fish collected in areas without direct
contamination (Amico et al., 1979), whereas much lower ratios have been
found for marine organisms in areas with more direct contaminant inputs
(Albaiges et al., 1987, Contardi et al., 1979, Fossato and Craboledda,
1980).
Based on these data, it appears that mesopelagic fish at the 106-Mile Site
have organic-contaminant body burdens less than or similar to those found
in fish from other continental slope waters and much less than fish of
coastal waters. Sewage-sludge disposal at the 106-Mile Site is only one of
several sources of PCB and pesticides and has not caused greater
contaminant body burdens in resident fish than those found at reference
stations. McVicar et al. (1988) recently found a similar no-effects
relationship between sewage-sludge dumping in the North Sea and the
prevalence of fish diseases. More definitive, conclusions on the biological
impact of sewage-sludge disposal at the 106-Mile Site might be made after
34
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the complimentary trace-metal data become available and after additional
surveys are conducted.
5.2 RECOMMENDATIONS
Based on the results of this study, myctophids appear to be good indicators
of exposure to chlorinated hydrocarbons and, therefore, myctophids should
be considered as potential biomarkers of long-term biological affects
resulting from sludge dumping at the 106-Mile Site.. However, before
myctophids can be used to assess the effects of sewage-sludge dumping at
the 106-Mile Site, more information is needed on the body burdens in fish
not impacted by dumping at the 106-Mile Site. This requires a more
thorough understanding of the distribution of contaminant body burdens in
waters outside the influence of the 106-Mile Site (i.e., background body
burdens) and the identification of contaminant gradients. These background
data would also provide critical information on the long-range transport
and fate of chlorinated hydrocarbons in open ocean waters. Several
recommendations are listed below regarding future studies of myctophids as
indicators of organic-contaminant exposure and effects.
• The use of myctophids as an indicator of long-term biological
effects of sewage-sludge dumping should be included in any future
monitoring plan for the 106-Mile Site.
• Any future field collections of myctophids should have complimentary
contaminant distribution data from whole water, particulate,
microlayer, and plankton samples. The additional information would
enhance our ability to relate contaminant body burdens to
contaminant transport and fate, and routes of exposure to the
organism.
36
-------
• The list of organic contaminants should include PCB and chlorinated
pesticides, and possibly PAH metabolites. Consideration should be
given to PCB/pesticide analysis by negative ion GC/MS, a method that
would increase sensitivity over conventional GC/ECD analyses, and
would also provide positive identification of these analytes.
• The distribution of contaminant body burdens should be determined in
myctophids collected at several sites beyond the influence of the
106-Mile Site as determined from physical oceanographic data.
Sampling design should include a transect(s) from coastal waters to
establish the existence of gradients.
• The background data should be used to estimate the body burdens that
would be expected in myctophids at the 106-Mile Site in the absence
of sewage-sludge dumping. The background body burdens can be used
to establish null hypotheses regarding the effects of sewage-sludge
dumping at the 106-Mile Site.
• Future field activity should be guided by advice from recognized
experts in the behavior and collection of myctophids to ensure
sampling success. The trauma of the fish could be minimized by
reducing the tow duration (<20 min.) and speed (2-4 knots), and
conducting more frequent trawls.
The June 1989 myctophid survey was joint NOAA/EPA monitoring effort.
Cooperation between NOAA and EPA will continue to yield comprehensive and
cost effective monitoring programs.
6.0. REFERENCES
Albaiges,J., A. Farran, M. Solar, A. Gallifa and P. Martin. 1987.
Accumulation and distribution of biogenic and pollutant
hydrocarbons, PCBs and DDT in tissues of western Mediterranean
fishes. Marine Environ. Res. 22:1-18.
Amico, V., G. Impellizzeri, G. Oriente, M. Piattelli, S. Scinto and C.
Tringali. 1979. Levels of chlorinated hydrocarbons in marine
animals from the central Mediterranean. Mar. Pollut. Bull.
10:282-284.
Battelle. 1988. Phase 4 Work/Quality Assurance Project Plan for the
National Status and Trends Mussel Watch Program. Prepared for
NOAA by Battelle Ocean Sciences. Contract No. 50-DGNC-5-00263.
Bayona, J.M., J. Albaiges, A.M. Solanas, and M. GrifolT. 1986.
Selective aerobic degradation of linear alkyl benzenes by pure
microbial cultures. Chemoshere 15:595-598.
Boehm, P.D. 1983. Coupling of particulate organic pollutants between
37
-------
the estuary and continental shelf and the sediments and water
column in the New York Bight region. Can. J. Fish. Aquat. Sci
40:262-276.
Contardi, V., R. Capelli, T. Pellocani and 6. Zanicchi 1979. PCBs and
chlorinated pesticides in organisms from the Ligurian Sea. Mar.
Pollut. Bull. 10:307-311.
Ecological Analysts. 1983. Special Permit Application for the Sewage
Sludge from Twelve New York City Water Pollution Control Plants at
the 12-Mile Site. A report prepared for the New York City
Department of Environmental Protection.
EPA. 1989. Proceedings of the Ocean Dumping Workshop 106-Mile Site EPA
Report 503/9-89/009.
EPA. 1992a. Final Draft Monitoring Plan for the 106-Mile Deepwater
Municipal Sludge Site. Environmental Protection Agency. EPA 842-
S-92-009.
EPA. 1992b. Final Draft Implementation Plan for the 106-Mile Deepwater
Municipal Sludge Site Monitoring Program. Environmental
Protection Agency. EPA 842-S-92-010.
EPA. 1992c. Final Report for Near-field 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.
Eganhouse, R.P., D.P. Olanguer, B.R. Gould, and C.S. Phinnely. 1988.
Use of molecular markers for the detection of sewage sludge at
sea. Marine Environ. Res. 25:1-22.
Eganhouse, R.P., E.G. Ruth, and I.R. Kaplan. 1983. Determination of
long-chain alky!benzenes in environmental samples by argentation
thin-layer chromatography/high resolution mass spectrometry and
gas chromatography/mass spectrometry. Anal. Chem. 55:2120-2126.
Fossato, V.U. and L. Craboledda. 1980. Chlorinated hydrocarbons in
organisms from the Italian coast of the Northern Adriatic Sea.
Ves. Journees Etud. Pollutions, CIESM, 169-174.
Harvey, G.R., H.P. Miklas, V.T. Bowen, and W.G. Steinhauer. 1974.
Observations on the Distribution of Chlorinated Hydrocarbons in
Atlantic Ocean Organisms. J. Marine Res. 32:103-118.
Krahn, M.M., L.K. Moore, C.A. Wigren, S. Chan, and D.W. Brown. 1988.
High performance liquid chromatographic method for isolating
organic contaminants from tissue and sediment extracts. J.
Chromat. 437:161-175.
38
-------
MacLeod, W.D., L.S. Ramos, A.J. Friedman, D.6. Burrows, P.6. Prohaska,
D.L. Fisher, and D.W. Brown. 1981. Analysis of residual
chlorinated hydrocarbons, aromatic hydrocarbons and related
compounds in selected sources, sinks and biota of New York Bight.
NOAA Tech. Memo. OMPA-6. NOAA Office of Marine Pollution
Assessment, Boulder, CO. 128p.
McVicar, A.M., D.W. Bruno, and C.O. Fraser. 1988. Fish diseases in the
North Sea in relation to sewage sludge dumping. Marine Pollution
Bull.
Murray, A.P. and C.F. Gibbs. 1987. Linear alky! benzenes (LABs) in
Sediments of Port Phillip Bay (Australia). Marine Environ. Res.
23:65-76.
Moyle, P.B. and J.J. Cech. 1987. Fishes: An Introduction to
Ichthyology. Prentice Hall. Englewood Cliffs, NJ. p. 266.
Weaver, G. 1984. PCB Contamination in and around New Bedford, Mass.
Environ. Sci. Techno!. 18:22A-27A.
39
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APPENDIX A. DATA QUALITY REQUIREMENTS AND QUALITY CONTROL RESULTS
Accuracy of the chemical data and assessment of the quality of the chemical!
data set are guided by quality control (QC) procedures described in
Battelle standard operating procedures (SOPs) listed in the Work Plan for
WA 38. Accuracy is ensured by the analysis of procedural blanks and
matrix spike samples. Laboratory extraction efficiencies were monitored by
tracking the recovery of internal standard and surrogate compounds.
Precision was determined by analysis of duplicate extractions.
Matrix spike and matrix.spike duplicate extraction recoveries and
procedural blanks are listed in Tables A-l and A-2. Surrogate recoveries
are listed in Tables A-3 and A-4.
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TABLE A-l. RESULTS OF PROCEDURAL BLANKS (PB), MATRIX SPIKES (MS), AND MATRIX SPIKE
DUPLICATES (MSD) FOR PCB AND PESTICIDES.
PCB/Pesticide
CL2(08)
HCB
LINDANE
CL3(18)
CL3(28)
HEPTACHLOR
CL4(52)
ALDRIN
CL4(44)
HEPTACHLOREPOXID
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)
MIREX
CL7(170)
CL8(195)
CL9(206)
CL10(209)
HV01 PB
(ng)
ND
0.039
ND
ND
ND
ND
ND
ND
2.309
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
HV04 PB
(ng)
ND
ND
0.055
ND
ND
ND
ND
ND
2.752
ND
ND
ND
ND
ND
ND
ND
ND
0.048
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
11.818
ND
ND
RECOVERY (%)
HV05-MS HV06-MSD
467.81b
19.06b
108.29,
131. 54b
115.59.
120. 34D
118.73.
127. 96b
115.45,
122. 04b
83.72
96.04
77.76
92.26
106.32
89.97,
123. 84b
100.95
92.71.
154. 79b
128. 51b
73.20
87.11
50.84
68.91
66.17
71.15
51.50
49.06
88.27
43.29
24.97
25.54
285. 15b
9.63b
98.33
no. 07
95.61
101.30
102.41.
121. 98b
95.88
103.28
' 72.03
77.66
61.50
72.65
83.07
107.12
100.34
85.45
77.06
92.88
105.29
64.06
74.81
34.08
55.67
52.31
56.84
36.61
39.81
92.61
34.69
21.24
21.42
MEAN
376
14
103
121
106
111
111
125
106
113
78
87
70
82
95
99
112
93
85
124
117
69
81
42
62
59
64
44
44
90
39
23
23
%RPDa
49'
66 %
10
18
19
17
•*• * 4.
15
5
19
17
15
21
23
24
25
' 17 •
21
17
18
50
20
13
15
39
21
23
22
34
21
5
+J
22
16
18
RPD = 2 * (MS - MSD)/(MS + MSD)) * 100.
'alue is outside acceptable recovery range (20-120%).
A-2
-------
-------
TABLE A
,-2. RESULTS OF PROCEDURAL BLANKS (PB). MATRIX SPIKES (MS), AND MATRIX SPIKE
DUPLICATE (MSD) RECOVERY VALUES FOR PAH AND LAB.a'b
PAH/LAB
naphthalene
2-methyl naphthalene
1-methylnaphthalene
biphenyl
2, 6-dimethyl naphthalene
acenaphthylene
acenaphthene
2,3 , 5-trimethyl naphtha! ene
fluorene
phenanthrene
anthracene
.-methyl phenanthrene
fluoranthene
jyrene
>enz[a]anthracene
:hrysene
>enzo [b] f 1 uoranthene
)enzo[k] fluoranthene
>enzo(e)pyrene
)enzo(a)pyrene
Derylene
indeno[l,2,3-c,d]pyrene
I ibenz [a, h] anthracene
)enzo[g,h,i]perylene
1 -phenyl decane
-phenyl undecane
-phenyl dodecane
-phenyl tridecane
-tetradecyl benzene
8-naphthalene
10-acenaphthene
12-perylene
-phenyl nonane
HV01PB
(ng)
11.90
5.47
4.33
NO
ND
ND
ND
ND
ND
ND
ND
ND
ND
3.46
ND
5.01
ND
ND
ND
ND
ND
ND
ND
ND
21.95
ND
5.88
25.60
110.47
Recovery (%)
HV04PB HV05 MS
(ng)
18.21
6.62
ND
ND
ND
ND
ND
ND
ND
2.9
ND
ND
5.61
5.26
ND
5.54
4.96
2.69
3.25
2.49
ND
ND
ND
ND
ND
ND
ND
2.89
34.69
92
103
101
101
103
101
81
78
78
54
42
61
54
49
299a
279a
Oa
Oa
132a
52
88
Oa
Oa
162a
104
96
79
87
78
394a
494a
32
439a
HV06 MSD MEAN
95
109
108
106
109
106
84
81
79
55
79
61
51
46
388a
363a
46
0
137a
95
90
0
0
172a
105
95
76
86
77
281a
360a
23
334a
93
106
104
104
106
103
83
80
79
54
61
61
52
48
344
321
23
0
135
74
89
0
0
167
105
96
77
87
78
337
427
27
38
%RPD
3
6
7
5 '
6 %
4
4
3
2
1
61
1
5
6
26
26
100
o
4
59
2
0
n
\s
6
1
1
4 .
1
2
33
31
34
27
value is outside acceptable recovery range (20-120%).
%RPD = 2 * (MS - MSD)/(MS + MS.D)) * 100
A-3
-------
TABLE A-3. SURROGATE (DBOFB) RECOVERIES FOR PCB/PESTICIDE ANALYSIS
Sample ID
Recovery (%)
HV01 PB
HV04 PB
AAL088A2
AAL089A2
AAL091A2
AAL090A2
AAL092A2
AAL093A2
AAL094A5
AAL094A2 .
AAL094A4
AAL095A2
AAL096A2
AAL096A4
105.35
67.45
116.86
101.97
96.91
119.96
82.82
17.593
82.91
86.04
91.40
23.11
23.08
57.83
aVa!ue is outside acceptable recovery range (20-
120%).
A-4
-------
TABLE A-4. SURROGATE RECOVERIES (%) FOR PAH AND LABa«b'c.
Sample ID
HV01 PB
AAL088A2
AAL089A2
AAL090A2
AAL091A2
AAL092A2
AAL093A2
AAL094A5
HV04 PB
AAL094A2
AAL094A4
AAL095A2
AAL096A2
AAL096A4
Sample Dry
Weight (g)
1.000
1.141
3.572
3.507
1.582
2.820
4.575
3.681
1.000
2.868
2.585
2.837
2.659
2.523
d8-N
91
86
83.
320b
77h
285b
35.
457b
61
89
97K
247b
228b
194b
dlO-A
93
93
94K
414b
83.
400b
38K
629b
74h
134b
142b
305b
288b
242b
d!2-B(a)P
96
92
79
32
85
28.
3b
Ob
NS
NS
NS
NS
NS
NS
d!2-P
99
92
76
26
84
21.
4b
104
94
34
39
32
34
28
1-PN
101
104
102,.
i*
525b
93L
I*
464b
50 .
578b
64
117L
l»
126b
107
120L
!•*
122b
ad8-N = d8-naphthalene
dlO-A = dlO-acenaphthene
d!2-B(a)P = d!2-benzo(a)pyrene
d!2-P = d!2-perylene
.1-PN = 1-phenyl nonane
Rvalue is outside acceptable range (20-120%).
NS = the surrogate was not spiked in the sample,
A-5
-------
-------
APPENDIX B. TRAWL LOCATION LOGS
-------
-------
BATTELLE OCEAN SCIENCES
Work Assignment 38
G3811
Trawl Location Log
TATION IDENTIFICATION
Station Number I
(X or X--XXX)
Date 11 oc*, &(
DD MM YY
U1PLING LOCATION Q)
Start of Tow
U*\ 5-7.0 TD2 4-2153.4. Lat
(xxxxx.x) (xxxxx.x) DD MM.MM
Lon "72
DDD MM.MM
End of Tow
TDl -2.4,11^.0 TD2
(xxxxx.x) (xxxxx.x)
Bottom Depth
Tow Depth
. 3 Lat ag, 4.5 __j__.N Lon -g 2J.
DD MM. MM
(xxx)
( XXX )
DDD MM. MM
Mean Wire Out -
(xxx)
No. of Myctophids 13 Kfc*jfc
( XXX ) F=ot2.
Start Time ,^4. : o^ (24 Hour clock) End Time OE> : 2^ ( 2 4 Hour clock
HH MM HH MM
y«PLING LOCATION 2
Start of Tow
TDl
KJ
o
TD2
(XXXXX.X
End of Tow
TDl
(XXXXX.X)
K|t=-T is
i"
Lat N Lon W
DD MM.MM DDD MM.MM
TD2
xxxxx.x) (xxxxx.x)
Bottom Depth
Lat N Lon W
DD MM.MM DDD MM.MM
m Mean Wire Out
(xxx)
Tow Depth m
(xxx)
(xxx)
No. of Myctophids Q
( xxx )
Start Time 0(0 '• 4n ( 24—Hour clock) End Time :
HH MM ' HH MM
24-Hour clock)
RECORDER
Name
ID Number 32.11.
: White- DAT[A MGR
Yellow- PROQgktt MANAGER
B-2
pink- FIELD PARTY;
-------
-------
BATTELLE OCEAN SCIENCES
Work Assignment 38
G3811
Trawl Location Log
'ATION IDENTIFICATION
Station Number I
(X or X-XXX)
Date
DD MM YY
J1PLING LOCATION 3
Start of Tow
TD2
(XXXXX.X)
End of Tow
TD1
(xxxxx.x)
DD MM. MM
Lon 12
ODD MM. MM
TD2
(xxxxx.x) (xxxxx.x)
Bottom Depth tSo4-im Mean Wire Out
Lon
DD MM. MM ODD MM. MM
Tow Depth
(xxx)
m
(xxx)
( xxx )
No. of Myctophids Q
(xxx)
S3U. . u
Start Time oq_: ifj_(24 Hour clock) End Time _H_ :_££>_( 2 4 Hour clock
HH MM HH MM
NQ
^MPLING LOCATION
XXXXX.X
End of Tow
TD1
(xxxxx.x) (xxxxx.
Bottom Depth
Tow Depth
Lat N Lon _W
DD MM.MM . DDD MM.MM
Lat __ N Lon W
DD MM.MM DDD MM.MM
Mean Wire Out .
Start Time
HH MM
(xxx )
(24-Hour clock) End Time
(xxx )
tophids Q
(xxx)
(24—Hour clock)
HH MM
RECORDER
Name
ID Number 37-U . IQ
White- DA'JA MGR
'J
Yeli'ow- PROGRAM MANAGER
B-3
Pink- FIELD PARTY)
-------
BATTELLE OCEAN SCIENCES
Work Assignment 38
G3811
Trawl Location Log
STATION IDENTIFICATION
Station Number I (
(X or X-XXX)
Date >S Q£
DD MM YY
SAMPLING LOCATION
Start of Tow
TD1
TD2
(xxxxx.x)
End of Tow
TD1 Z
(xxxxx.x)
TD2
(XXXXX.X)
(XXXXX.X)
Bottom Depth 2,5^.7 1
(xxx)
Tow Depth 55 2^ Lon
(xxxxx.x) (xxxxx.x) DD MM.MM DDD MM.MM
I2.&O PM "^"If
Bottom Depth 2^3-f mfc-q^>lean Wire Out "
(xxx) (xxx)
Tow Depth 34,2. m
(xxx)
No. of Myctophids 30
(xxx)
Start Time zg> ; i (24-Hour clock) End Time 2J : IS. ( 24-Hour clock
HH MM HH MM
, RECORDER
Name
ID Number 32.11. I
White- DATA MGR
fellow- PROGRAM MANAGER Pink- FIELD PARTY]
B-4
-------
BATTELLE OCEAN SCIENCES
Work Assignment 38
G3811
Trawl Location Log
ATION IDENTIFICATION
Station Number i
(X or X-XXXr
Date is ofe PA
DD MM YY
MPLING LOCATION
Start of Tow
TDl
TD2
(xxxxx.x)
End of Tow
(xxxxx.x)
Lat 3& 52
DD MM. MM
ODD MM. MM
TD2
35 55 2&N Lon iz
DD MM. MM ODD MM. MM
(xxxxx.x) (xxxxx.x)
Bottom Depth I3eo*m Mean Wire Out
Tow Depth
(xxx)
2fT-M~*t
4*5 ^m '^
(xxx)
Cxxx)
No. of Myctophids 3e>o
(xxx)
Start Time "2.1 : 4£> ( 24 Hour clock) End Time Z2. ' 4-d, ( 2 4 Hour clock
HH MM ' HH MM
JMPLING LOCATION
Start of Tow
TDl
(XXXXX.X
End of Tow
TDl
TD2
TD2
(XXXXX.X
(XXXXX.X
(XXXXX.X)
Bottom Depth
Lat N Lon W
DD MM.MM ' DDD MM.MM
Lat N Lon W
DD MM.MM DDD MM.MM
m Mean Wire Out
Tow Depth
(xxx)
m
(xxx
No. of Myctophids
Start Time
(xxx)
(24—Hour clock) End Time
(xxx )
(24-Hour clock)
HH MM
HH MM
RECORDER
ID Number 32.11
i White- DAT MGR
^
Yellow- PROGRAM MANAGER Pink- FIELD PARTY!
8-5
-------
BATTELLE OCEAN SCIENCES
Work Assignment 38
G3811
Trawl Location Log
STATION IDENTIFICATION
Station Number
(X or X-XX
OF=
Date j
DD MM YY
SAMPLING LOCATION
Start of Tow
TDI 2.kS2.^.0 TD2 4-l=na.7_ Lat 31 3Q g£^ Lon 15 J£g, _!$
(xxxxx.x) (xxxxx.x) DD MM.MM DDD MM.MM
End of Tow
TDI
( xxxxx. x)
1 . s TD2
( xxxxx.
Bottom Depth yj
(xxx)
_ . , "asTfcP
Tow Depth TOW m
(xxx
Lat 37 30 ^pN Lon
DD MM.MM DDD MM.MM
Mean Wire Out -
(xxx)
No. of Myctophids TbTAi-21
(xxx)
Start Time 12. : 4.1 (24 Hour clock) End Time Z3 =43 (24 Hour clock
HIT MM HH MM
SAMPLING LOCATION
Start of Tow
TD2
Lat
( XXXXX . X )
DD MM . MM
Lon -^3 14 3 W
DDD MM. MM.
(XXXXX.X)
End of Tow
TDl 2-^ST.fo.l TD2 IS4-13.4 Lat •£_ 5^ gaN Lon -73 2A
(xxxxx.x) (xxxxx.x) DD MM.MM DDD MM.MM
Bottom Depth ic^oo4..im Mean Wire Out -
(xxx) (xxx)
Tow Depth 4-Q m
(xxx)
No. of Myctophids
(xxx
24
Start Time ^ ; 03 (24-Hour clock) End Time O1 : pc, (24-Hour clock)
HH~ MM HH MM
RECORDER
ID Number
White- DATA MGR^Yellow- PROGRAM MANAGER Pink- FIELD PARTY;
B-6
-------
BATTELLE OCEAN SCIENCES
Work Assignment 38
G3811
Trawl Location Log
TATION IDENTIFICATION
Station Number 7
Date 1
(X or X-XXX)
DD MM YY
AMPLING LOCATION
Start of Tow
TD1
TD2
(xxxxx.x)
End of Tow
TD1
(xxxxx.x)
37 30
DD MM. MM
Lon -73,
DDD MM. MM
. TD2 l&3^-T.ft Lat 3^ jfc j^N Lon -73
(xxxxx.x) (xxxxx.x) DD MM. MM DDD MM. MM
Bottom Depth
m Mean Wire Out
Tow Depth _25__m
(xxx)
(xxx) (xxx)
No. of Myctophids
(xxx)
Start Time p\ : 33, (24 Hour clock) End Time 62, '• 3X (24 Hour clock
HH MM HH MM
IPLING LOCATION
(xxxxx.x)
XXXXX.X
Lat N Lon W
DD MM.MM DDD MM.MM
Lat N Lon W
DD MM.MM DDD MM.MM
Bottom Depth
m
Wire .Out
Tow Depth
(xxx)
m
(xxx)
(xxx)
Start Time
HH MM
No. of Mycto>hids
(24—Hour clock) End Time
HH MM
(xxx)
(24-H>t«r clock)
RECORDER
Name
ID Number
(White- DATA MGR Yellow^ PROGRAM MANAGER Pink- FIELD PARTY)
B-7
-------
BATTELLE OCEAN SCIENCES
Work Assignment 38
G3811
Trawl .Location Log
STATION IDENTIFICATION
Station Number 3" SAESrAsso SEA Date 12 C4. &9_
(X or X-iXXX) DD MM YY
SAMPLING LOCATION I
Start of Tow
TDl 2-£»gio4-. 1 TD2 14-8^4-,2. Lat g& 44. 4QN Lon "7{ Ol
(xxxxxlx) (XXXXX.X) DD MM.MM DDD MM.MM
End of Tow
TD2 4-1 ~7 c. «=..-? Lat 3^ 43 s$N Lon T|
(xxxxx.x) (xxxxx.x) DD MM.MM DDD MM.MM
' Bottom Depth m Mean Wire Out
(xxx) (xxx)
Tow Depth _£-C£L_m No. of Myctophids 5
(xxx) (xxx)
Start Time -J-5-:_^e^24 Hour clock) End Time |fe ; c^ (24 Hour clock
HH~ MM" HH MM
SAMPLING LOCATION L_
Start of Tow
TD1 2Jbq l I . o TD2 411^7..S Lat 3^ 47. Sc-N Lon ~il
(xxxxx.x) (xxxxx.x) DD MM.MM DDD MM.MM
End of Tow
3.3 TD2 4-l-?e>d..5 Lat ^ ^ epN Lon ~7| fj7
(xxxxx.x) (xxxxx.x) DD MM.MM DDD MM.MM
Bottom Depth m Mean Wire Out
j lx^x] ^xxx!,
j Tow Depth ^r&-f m No. of Myctophids
j ^ i ,, (xxx) • (,xxx)
I Start Time Il_:jb3_( 24-Hour clock) End Time | c\ ; \e^( 24-Hour clock)
j HH MM HH MM
I ' ,. ,. ; ,
RECORDER '
Name ~yf. ^ ~w\ ^^—~^ ID Number ^n.ic
i - • --t j • • "T"]-"
White- DATA.MGR Yellow- PROGRAM MANAGER Pink- FIELD PARTY)
B-8
-------
BATTELLE OCEAN SCIENCES
Work Assignment 38
G3811
Trawl Location Log
ATION IDENTIFICATION
Station Number
(X or X-
Date iZ
DD MM YY
MPLING LOCATION g
Start of Tow
TD1 •z.e>AAO.?> TD2 41155.3 Lat 3^ £j gjrjt Lon
(xxxxx.x) (xxxxx.x) DD MM.MM DDD MM.MM
End of Tow
TD1 'Zg.ftlZ.Z TD2 4-1-13ft."? Lat ^ ^ ^N Lon -jo £\ 1OW
(xxxxx.x) (xxxxx.x) DD 'MM.MM DDD MM.MM
Bottom Depth 77go Fm Mean Wire Out
(xxx) (xxx)
Tow Depth
( xxx )
_m No. of Myctophids g
(xxx)
Start Time _2o_:j£_(24 Hour clock) End Time '-j\ : \et (24 Hour clock
HH MM HH MM
WPLING LOCATION
Start of Tow
TD1 2.5 & faa. t TD2
(xxxxx.x) (xxxxx.x)
End of Tow
TD1
TD2
(xxxxx.x) (xxxxx.x)
Bottom Depth
(xxx)
Tow Depth ZO
( xxx )
20.
DD MM.MM
Lon
DDD MM.MM
Lon -70
DD MM.MM DDD MM.MM
Mean Wire Out 4oom
(xxx)
No. of Myctophids |
(xxx)
Start Time 2JT : ^2. (24-Hour clock) End Time 2.3 ; e,;. (24—Hour clock)
Iffi MM HH MM
RECORDER
Name
ID Number 32.U.IQ
(White- DATA MGR
. 1 ow// PROGRAM MANAGER
B-9
pink- FIELD PARTY;
-------
BATTELLE OCEAN SCIENCES
Work Assignment 38
G3811
Trawl Location Log
STATION IDENTIFICATION
Station Number 4- ( AQNJI K]ET
(X or X-XXX)
Date 14.
DD MM YY
SAMPLING LOCATION (T)
Start of Tow
TD1
TD2
(XXXXX.X)
End of Tow
TD1
(XXXXX.X)
Lat sg n 4-oN Lon ~JO 42
DD MM.MM ODD MM.MM
>-7 . I TD2 4.3^6^, .?_ Lat 3<=} |fe 10 N Lon ~7o 4jj 40
( xxxxx. x) ( xxxxx. x) DD MM. MM DDD MM. MM
Bottom Depth I4547.O m Mean Wire Out
( xxx ) ( xxx )
Tow Depth (aoc, m
(xxx)
No. of Myctophids
( xxx )
Start Time 05 ; 55 (24 Hour clock) End Time 01 :2.& (24 Hour clock
HH MM HH MM
SAMPLING LOCATION
Start of Tow
TD1
(XXXXX.X)
End of Tow
TD1
TD2
TD2
Lat
XXXXX . X )
Lon °
.
' CD ...... MM . MM"
-
DDD MM . MM
(xxxxx.x) (xxxxx.x)
Bottom Depth
Lat 3q >Z loN Lon TO 47
DD MM.MM DDD MM.MM
Tow Depth
( xxx )
m Mean Wire Out
(xxx) (xxx
No. of Myctophids 24
(xxx)
Start Time oq :01 (24—Hour clock) End Time 10 ;QI (24—Hour clock)
HH MM - HH MM
RECORDER
Name
L/l
ID Number 32.11.10
White- DATA MGR
Yellow- PROGRAM MANAGER
B-10
Pink- FIELD PARTY)
-------
BATTELLE OCEAN SCIENCES
Work Assignment 38
G3811
Trawl Location Log
•ATION IDENTIFICATION
Station Number
A. (£OIAI IJE
(X or X-XXX
Date J4
DD MM YY
U1PLING LOCATION
Start of Tow
TD1
TD2
(XXXXX.X)
End of Tow
TD1 z
(XXXXX.X)
DD MM. MM
Lon -fo 4
DDD MM . MM
TD2
( xxxxx. x)
'(xxxxx.x)
Lon _
DD MM. MM DDD MM. MM
Bottom Depth l4-S&3.ftm Mean Wire Out
(xxx) (xxx)
Tow Depth tXO m
(xxx)
No. of Myctophids
( xxx )
Start Time n ; zi (24 Hour clock) .End Time IZ : 37 (-24 Hour clock
HH MM" HH MM
kMPLING LOCATION
Start of Tow
TD1
TD2
. Lat . N Lon __ W
(xxxxx.x) (xxxxx.x) DD MM.MM DDD MM.MM
End of Tow
TDl
TD2
Lat _ __ N Lon _ _ _ W
DD MM. MM DDD MM . MM
(xxxxx.x) (xxxxx.x)
Bottom Depth m Mean Wire Out
Tow Depth
m
(xxx)
No. of Myctophids
xxx
Start Time
24-Hour clock) Ertd Time
( xxx )
24—Hour clock)
HH MM
HH MM
RECORDER
Name
ID Number 37//,
.White- DATA MGR Yellow- PROGRAM MANAGER Pink- FIELD PARTY
-------
-------
APPENDIX C. HYDROGRAPHIC PROFILES
-------
-------
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