Contaminant Transport from Elliott
and Commencement Bays
February 1987
Submitted to
EPA. Region X. Puget Sound Project
1200 6th Avenue. Mail Stop 433
Seattle. Washington 98101
Submitted by
Pacific Marine Environmental Laboratory/ ERL NOAA
"600 Sand Point Way NE
Seattle. Washington 98115

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CONTAMINANT TRANSPORT FROM ELLIOTT AND COMMENCEMENT BAYS
FINAL REPORT
AUGUST 1987
H.C.
E.T.
T.S.
C.A.
R.A.
T.L.
M.F.
P.P.
D.J.
A.J.
D. A.
Curl, Jr.,
Baker
Bates
Cannon
Feely
Geiselman
Lamb
Murphy
Pashinski
PauLson
Tennant
Project Manager
>300,
Prot^S°fu-S.
^6 for "~'Q8
J£-]

I99f

Seattle
Wa
9810i
Prepared for:
EPA, Region X, Puget Sound Estuary Program
1200 6th Ave., Mail Stop 433
Seattle, WA 98101
Submitted by:
Pacific Marine Environmental Laboratory
Seattle, Washington 98115
September 1986
Contribution No. 903 from NOAA/Paciflc Marine Environmental Laboratory
U.S. EPA LIBRARY REGION 10 MATERIALS
1
RXOD

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TABLE OF CONTENTS
I.	Overview and Executive Summary	1
1.1.	Executive Summary	1
1.2.	Introduction	11
1.3.	General Approach	15
II.	Results	16
11.1.	Elliott Bay	16
II. 1.1 Meteorological Setting	16
11.1.2.	Hydrographic Setting	17
11.1.3.	Physical Oceanography	21
11.1.3.1.	Salinity		29
11.1.3.2.	Currents		35
11.1.4.	Particulate Matter Transport	51
II.1.4.1. April 1985	57
II. 1.4.2. January 1986					76
11.1.4.3.	SPM - Salinity Relationships	77
II. 1.4.4. SPM Loading and Vertical Mass Flux	79
II. 1.5. Trace Metals and Organics in Elliott Bay	80
11.1.5.1.	Trace Metals	80
11.1.5.2.	Toxic Organics	138
11.1.5.3.	Summary...	147
11.2.	Commencement Bay	151
11.2.1.	Hydrographic Setting	154
11.2.2.	Physical Oceanography	154
11.2.2.1.	Salinity	154
11.2.2.2.	Currents	155
11.2.3.	Particulate Matter Transport	166
II.2.3.1. SPM - April 1985	166
11.2.4.	Toxic Trace Metals and Organics in Commencement Bay	167
11.2.4.1.	Toxic Trace Metals			167
11.2.4.2.	Toxic Organics		133
11.2.4.3.	Summary	192
References			194
Appendix I: Particulate Chemistry Data for Elliott Bay During
April 1985 (wt./vol.)			198
Appendix II: Particulate Chemistry Data for Elliott Bay During
April 1985 (wt./wt.)	201
Appendix III: Particulate Chemistry Data for Elliott Bay Bay During
January 1986 (wt./vol.)			204

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Appendix IV: Particulate Chemistry Data for Elliott Bay During
January 1986 (wt./wt.)			206
Appendix V: Particulate Chemistry Data for Commencement Bay During
April 1985 (wt./vol.)	208
Appendix VI: Particulate Chemistry Data for Commencement Bay During
April 1985 (wt./wt.)			210
Appendix VII: Dissolved Data for Elliot Bay During April 1985	212
Appendix VIII: Dissolved Data for Elliott Bay During January 1986	213
Appendix IX: Dissolved Data for Commencement Bay During April 1985	214
Appendix X: Trace Organic Compounds Quantified During this Project	215
Appendix XI: Trace Organics Collected by Centrifuge During April 1985..216
Appendix XII: Trace Organics Collected by Sediment Traps in 1985	217
Appendix XIII: Trace Organics Collected by Centrifuge During
January, 1986	218
Appendix XIV: Storm Drain Calculations	219
Appendix XV: Trace Metals in Sediment Trap Samples	220
Appendix XVI: Elliott Bay Plume Mapping Data	221
Appendix XVII: Quality Assurance Project Report	224

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TABLES
Table II. 1. Mooring Locations and Deployment Dates	28
Table II.2. CTD Observations	28
Table II.3. Moored Instrument Statistics	30
Table II.4. Mass Loading of the Upper 2.0 m of Elliott Bay	81
Table II.5. Vertical Mass Flux at 50 m at Mooring PS8S01 during
the April, 1985 survey	81
Table II.6. Transport of Dissolved Trace Metals	95
Table II.7. Flux of total suspended matter and particulate metals
out of Elliott Bay (g/sec)			99
Table II.8. Transport of Cu, Zn and Pb out of Elliott Bay	131
Table II.9. Enrichments of Trace Metals in surface plumes in
Elliott Bay	..148
Table 11.10. Horizontal and Vertical Flux of suspended matter
and particulate trace metals in Elliott Bay
during April 1985	149
Table 11.11. Order-of-magnitude calculation of the flux of trace
metals from the Denny Way CSO during the
January 8th storm	149
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FIGURES
Figure I«l.	Map of Puget Sound: Elliott Bay and Commencement Bay	12
Figure II. 1.	Discharge rates of the Duwamish River	18
Figure II.2.	Discharge of the Duwamish River at Tukwila	22
Figure II.3.	Discharge of the Denny Way CSO. 3-5 January 1986	24
Figure II.4.	Discharge of the Denny Way CSO. 8 January 1986	26
Figure II.5.	Salinity in Elliott Bay. March and July 1985	32
Figure II.6.	Surface salinity in Elliott Bay, April 1985	36
Figure II.7.	Salinity along Duwamish West Waterway, July 1985	38
Figure II.8. Salinity time series in Elliott Bay and Duwamish West
Waterway. March-July 1985	40
Figure II.9. Salinity difference time series in Elliott Bay and
Duwamish West Waterway, March-July 1985	42
Figure 11.10. Vector time series of low pass filtered winds at
Three Tree Point, March-July 1985	44
Figure 11.11. Time series of currents in Elliott Bay and Duwamish
West Waterway, March-July 1985	46
Figure 11.12. Spectrum of near-bottom current speeds in the
Duwamish West Waterway, March-July 1985	48
Figure 11.13. Vector time series of low frequency currents in
Elliott Bay, March-July 1985	52
Figure 11.14. Progressive vector diagrams of currents in Elliott Bay....54
Figure 11.15. Stations sampled for suspended particulate matter
(SPM) in Elliott Bay, April 1985 and January 1986	58
Figure 11.16. Transects sampled for SPM in Elliott Bay, ApriL 1985
and January 1986	60
Figure 11.17. Vertical sections of SPM in Elliott Bay,
4-5 April 1985			62
Figure 11.18. Vertical sections of salinity in Elliott Bay,
4-5 April 1985	64
Figure 11.19. Vertical sections of SPM and salinity in Elliott Bay,
8-9 January 1986	66
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Figure 11.20. Near surface (2 in) SPM in Elliott Bay, 4 April 1985	68
Figure 11.21. Near surface (2 m) SPM in Elliott Bay,
8-9 January 1986	70
Figure 11.22. Near surface (2 in) salinity in Elliott Bay,
8-9 January 1986	72
Figure 11.23. Regressions of salinity and SPM in Elliott Bay,
April 1985 and January 1986	7A
Figure 11.24. Stations and transect locations for metal sampling
in Elliott Bay			82
Figure 11.25.	Hypothetical mixing curve for trace metals	86
Figure 11.26.	Distribution of particulate A1 in Elliott Bay	90
Figure 11.27.	Distribution of dissolved Fe in Elliott Bay	92
Figure 11.28.	Distribution of particulate Fe in Elliott Bay	96
Figure 11.29.	Distribution of dissolved Mn in Elliott Bay	100
Figure 11.30.	Distribution of particulate Mn in Elliott Bay	102
Figure 11.31.	Distribution of dissolved Cu in Elliott Bay	...106
Figure 11.32.	Distribution of particulate Cu in Elliott Bay	108
Figure 11.33.	Distribution of dissolved Zn in Elliott Bay	110
Figure 11.34.	Distribution of particulate Zn in Elliott Bay	114
Figure 11.35.	Distribution of dissolved Pb in Elliott Bay	116
Figure 11.36.	Distribution of particulate Pb in Elliott Bay	118
Figure 11.37.	Distribution of dissolved Ni in Elliott Bay	122
Figure 11.38.	Distribution of particulate Ni in Elliott Bay	124
Figure 11.39.	Distribution of particulate Cr in Elliott Bay	126
Figure 11.40.	Distribution of dissolved Cd in Elliott Bay	128
Figure 11.41. Regressions of salinity and dissolved trace metals
in near surface layer in Elliott Bay in 1980, 1981,
1985, 1986	132
Figure 11.42. Regressions of salinity and particulate trace metals
in near surface layer of Elliott Bay in 1980, 1981,
1985, 1986		134
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Figure 11.43. Sampling stations and PAH concentrations in Elliott
Bay, April 1985 and January 1986			140
Figure 11.44. PAH in Elliott Bay sediments	142
Figure 11.45. Station locations and moorings in Commencement Bay	152
Figure 11.46. Discharge of the Puyallup River: 10 year average
monthly ranges and averages	156
Figure 11.47. Surface salinity in Commencement Bay, March-April 1985...158
Figure 11.48. Salinity difference time series in Commencement Bay,
March-April 1985	160
Figure 11.49. Time series of currents in Commencement Bay,
March-April 1985			162
Figure 11.50. Time series of currents in Commencement Bay,
March-April 1985			164
Figure 11.51. Progressive vector diagrams of currents in Commencement
Bay, April 1985		168
Figure 11.52. Transect of TSM in Commencement Bay, April 1985	170
Figure 11.53. Transect of dissolved and particulate Fe in Commencement
Bay, April 1985	172
Figure 11.54. Transect of dissolved and particulate Mn in Commencement
Bay, April 1985	176
Figure 11.55. Transect of dissolved and particulate Cu in Commencement
Bay, April 1985	178
Figure 11.56. Transect of dissolved and particulate Zn in Commencement
Bay, April 1985	180
Figure 11.57. Transect of dissolved and particulate Pb in Commencement
Bay, April 1985				184
Figure 11.58. Transect of dissolved and particulate Ni in Commencement
Bay, April 1985	186
Figure 11.59. Transect of dissolved Cd in Commencement Bay,
April 1985	188
Figure 11.60. PAH in Commencement Bay	190
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ACKNOWLEDGMENTS:
We wish to acknowledge Che help of Scott Burger, Sharon Walker and Ken
Bloomstein for sample collection and Sharon Froberg. for data processing. We
appreciate the support and flexibility of the officers and crew of the NOAA
Ship McArthuir, especially Captain Fred Jones and Field Operations Officer
Walter Latimer.
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I. OVERVIEW AND EXECUTIVE SUMMARY
1.1 EXECUTIVE SUMMARY
Major sources of contamination to Puget Sound are concentrated in the
urban embayments. Most of these contaminants are particulates or adhere to
particles. If these particulates are dense, they tend to fall out of the
water column near the source; thus analysis of the sediment within urban
embayments can provide an indication of the level of contamination, and by
proximity, of the probable source of that contamination. The question remains
however, to what degree do contaminants move, or are transported, away from
the original source, out of the embayment, and are carried into the main basin
of the Sound. In other words, to what extent is incoming contamination
localized, or Sound-wide in nature. In order to determine this we attempted
to answer the following research questions:
1)	What is the relative importance of the surface, fresh water plume
versus the bottom resuspended (nepheloid layer)?
2)	How much does transport vary seasonally, particularly as affected by
winter runoff?
3)	Is there loss to the bottom from the surface plume?
4)	Are contaminants remobilized from the bottom sediments?
During spring and summer 1985, and again in January 1986, the Pacific
Marine Environmental Laboratory (PMEL) of NOAA made a series of observations
designed to determine to what degree contaminants in Elliott and Commencement
Bays could leave the bays and enter the main basin of Puget Sound.
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The approach employed in this study was to map the distributions of water
properties (salinity, suspended particulate matter or SPM, and toxic trace
metals and organics) during a period of high river runoff (April 4-5, 1985,
Elliott and Commencement Bay) and during combined sewer overflow (CSO) events
(January 8-9, 1986, Elliott Bay only) after heavy rainfall. Current meters
and sediment traps were deployed in Elliott Bay south of the Pier 90 anchorage
and in Commencement Bay in the outer, center of the bay. The current meters
provide a continuous record of salinity, temperature, current speed and
direction which allows a calculation of horizontal transport.
I.1.1 Physical Conditions
Elliott and Commencement Bays are similar in that they host a variety of
urban and industrial activities, are deep (150-200 m), and have similar shapes
with rivers at their heads. However, Commencement Bay has approximately half
the area of Elliott Bay. The waters of the bays are from two sources: large
volumes of deep, salty water from the main basin and small amounts of river
water which forms a brackish layer only a few meters deep within the bays.
The brackish water is formed by mixing of the two sources within the river
mouths. The two sources continue to mix as the upper layer flows out into the
bay, becoming progressively saltier.
During the April sampling period light rain fell Jless than 0.1 inch/day)
under light and variable winds. The mean monthly flow of the Green-Duwamish
River was 150% of the ten-year average for April and double the ten-year
average for the sampling period. During the January sampling period rainfall
was a quarter-inch per day or less, with somewhat stronger winds from the
south. River flow was 67% of the ten-year January average. Rainfall had been
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much lower Chan usual earlier, but 1.85 inches of rain £ell between
December 31 and January 5. River flow was unaffected but the Denny Way CSO
and six other CSOs overflowed during the sampling period (January 8-9). More
than 83,000 m3 of water was discharged by the CSOs over eight days. During
the same period the Duwamish River discharged 21.4 million m3. Thus the CSOs
were equal to about 0.4% of the river flow.
The current meter moorings were in place from March 27 until July 9 of
198S. The mean flow at 4 m depth was only 3 cm/sec (0.06 mph) toward the
west-northwest. This was equivalent to a mean transit time of 5 days from the
mouth of the Duwamish River to Four Mile Rock. At 100 m, one meter off the
bottom, the current was 0.8 cm/sec (0.02 mph) toward the southwest. The river
water layer was very thin, only two meters deep, with a salinity difference
more than sufficient to maintain a sharp vertical discontinuity.
1.1.2 Suspended Particulate Matter
If much of the contaminant load is associated with suspended particulate
matter (SPM), it is instructive to examine the surface distribution of SPM and
compare these distributions with the distribution of different pollutants.
The same approach can be taken with salinity. The primary sources of
contaminants are related to freshwater inputs.
In April 1985 the only source of SPM was the Duwamish River. Contours of
both salinity and SPM show that the river plume hugs the north and east sides
of Elliott Bay, exiting northwestward around Magnolia Bluff as it mixes with
saltier, cleaner main basin water. In January, the same general pattern is
seen, except that the Denny Way CSO is clearly a much more concentrated source
of SPM. Rough calculations based on flow rates and sediment concentration of
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the river and the CSO suggest that the Denny Way CSO contributed close to 30%
of the total SPM to the Bay.
Correlations between SPM and salinity (mixing curves) show that dilution
of the surface river plume by marine water from the main basin was the
principal factor in controlling the decrease of SPM in the bay; therefore SPM
loss by settling or other processes is insignificant. In the surface SPM and
salinity are inversely correlated because the SPM sources are controlled by
fresh water sources. In deep water, SPM and salinity are positively
correlated suggesting that the high turbidity of the deep water is caused by
movement of main basin deep water into the Bay rather than local
resuspension. The highest salinity water has the highest concentration of
SPM.
Calculations of the total amount of SPM in the surface layer in April
showed that nearly half of the SPM was in the upper half-meter; another thirty
percent was in the next half-meter. Sediment traps were used to calculate the
vertical loss or flux, which was 4% per day of the SPM in the 2 m deep
plume. Vertical flux is proportional to the total loading at any given
point. Since the mooring was located in the region of maximum loading, the
figure of 4% should be a maximum, and should decrease away from the mooring.
A likely average would be 2.5% per day. This means that most of the suspended
material is transported out of the Bay rather than being deposited within the
Bay. Approximately 90% of the SPM discharged to Elliott Bay leaves the Bay
for the main basin.
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1.1.3 Trace Metals
Since the maximum concentrations of contaminants were in the surface
layer, with only background levels at depth, and no evidence of resuspension
of bottom sediments, surface samples were taken to look for sources of toxic
trace metals and organics to the bay and to map their distribution. In
general, the highest concentrations of toxicants originated from the West
Duwamish Waterway, the north end of Harbor Island, the Denny Way CSO and the
Seattle waterfront including the King Street CSO. (The East Duwamish
Waterway, while a source of fresh water and SPM in January, was not notable as
a source of contaminants.)
In terms of total mass of material added to Elliott Bay, the West
Duwamish Waterway is the major contributor to the system followed by the Denny
Way CSO, Harbor Island waterfront and Seattle waterfront, in that order,
because of the differences in flow. In April the flow of the West Waterway
was 250 times that of the CSO; thus the West Waterway provided 56 times as
much dissolved zinc, 35 times as much dissolved copper and 20 times as much
particulate lead as the CSO. The West Waterway may be considered a chronic
source, the CSO an acute source.
Copper originates from plumbing, marine anti-fouling products, plating
plants and electrical wiring. In Elliott Bay soluble and particulate copper
had similar distributions. In April the Duwamish West Waterway (DWW) was a
principal source of particulate copper. However, during the heavy rainfall in
January, the DWW was overshadowed by surface runoff from the northern tip of
Harbor Island and the Denny Way CSO.
Zinc is quite soluble, originating from corrosion of galvanized products,
zinc-based paint and plating plants. The DWW, Harbor Island the Denny Way CSO
are all strong zinc sources in January.
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In contrast, lead exists primarily in the particulate form. It
originates as an aerosol in automobile exhaust, and from battery plants,
smelters and paint. However, dissolved lead can diffuse from strong sources
during light rainfall and to a greater extent during heavy rainfall. There
was a very poor correlation between salinity and dissolved lead
concentrations, indicating a multiplicity of sources, including atmospheric
deposition in January. The DWW is clearly the principal source of particulate
lead during high river runoff, probably collecting atmospheric deposition from
throughout its watershed. However, heavy rainfall flushed surface
particulates from Harbor Island and from the Denny Way CSO, as well as the
Seattle Waterfront. Particulate lead concentrations were 4-10 times the
dissolved lead concentrations.
Cadmium is an interesting element in Puget Sound in that the major source
is ocean water even though there is a source from plating plants, plastics,
paint and the electronics industry. In January, runoff from Harbor Island and
the Denny Way CSO exceeded oceanic concentrations by three and two times,
respectively. These relative increases are not nearly as high as they were
for other metals.
Of the contaminant trace metals, the strongest sources of cadmium, zinc
and lead were Harbor Island and the Denny CSO; nickel and chromium originated
mostly from the West Waterway and Denny CSO. An assessment of source
strengths and flow rates permits a calculation of the total contribution of
the West Waterway, versus other sources, to the trace metals leaving Elliott
Bay. In January the contribution of the West Waterway of dissolved metals
was: copper, 32%, zinc, 46% and nickel, 63%. For particulate metals the
contribution was: copper, 24%; zinc, 46%; lead, 29%; and nickel, 29%. The
Denny Way CSO and Harbor Island runoff contributed most of the remainders.
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A comparison was made of Che relative horizontal and vertical, fluxes of
suspended matter and trace metals in Elliott Bay during April 1985. The
vertical flux of all suspended matter is only 1.6Z of the horizontal flux.
For copper, it is 0.8% of the horizontal flux and for lead it is 2.4%. Thus,
just as with SPM, most of this contaminate material is leaving Elliott Bay for
the main basin.
1.1.4 Toxic Organic3
The concentration of PAH entering Elliott Bay from the Duwamish River in
April 1985 was very low (1 ug/g SPM), and is equivalent to values found in
Admiralty Inlet. Surface values averaged 5 ug/g. However, as a result of
urban runoff, values were much higher in source areas: 35 ug/g just off the
Denny May CSO, 18 ug/g at the mouth of the West Water and 11 ug/g along the
waterfront. The concentration of PAH on suspended particulates from near-
bottom waters in Elliott Bay averaged four times higher than on particulates
from the near-bottom waters in the main basin. Values in sediment samples are
indicative of long term sources; high values (up to 24 ug/g) are found in and
north of the West Waterway, along the Seattle waterfront, just off the Denny
CSO, at a point off Magnolia Bluff and at the Four Mile Rock dredge disposal
site. There is some evidence that PAH adheres to larger particles than do
trace metals and may remain closer to the source areas.
The concentrations of polychlorinated biphenyls (PCB) and DDT, DDD and
DDE in the water column were at, or below, limits of detection.
Concentrations of some PCB isomers were higher in January 1986 than in April
1985 in surface waters, suggesting that there is still some leakage and
subsequent runoff, but the concentrations were still quite low (less than
90 mg/g).
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1.1.5. Commencement Bay
The situation in Commencement Bay was similar to that in Elliott Bay.
Monthly mean flow in April 1986 was 133Z of the ten-year monthly average. As
in Elliott Bay, there is a very shallow, surface brackish layer only a few
meters thick. The river plume is compressed against the north shore on rising
tides and exits the bay down the center on falling tides. The maximum tidal
currents are larger than in Elliott Bay, occasionally reaching 40 cm/sec at
4 m depth and 20 cm/s near the bottom. The non-tidal flow shows a cross-bay
component as well as alternating periods of inflow and outflow. However, the
net transport is very low: 2.4 cm/sec (0.05 mph) at 4 m and 0.3 cm/sec
(0.01 mph) at 153 m. Water from the Puyallup River would take an average of
two days to reach Reston in April. Near bottom water would take an average of
eighteen days to cover the same distance. However, tidal excursions of a few
kilometers per tidal cycle increase the contact period with the bottom and
shoreline. It is clear from the coarser bottom sediments that tidal
resuspension allows fine particles to diffuse from the Bay, even if at a very
slow rate. This finding is supported by the presence of a thick (50 m) bottom
resuspension (nepheLoid) layer along the axis of the bay.
In general, the highest trace metal concentrations in Commencement Bay
were one-half to an order of magnitude less than in Elliott Bay. For example,
particulate lead ranged from 200-10,000 ng/L in Elliott Bay and from 400-
700 ng/L in Commencement Bay. Particulate copper showed an ever greater
disparity: 200-6,000 ng/L and 25-75 ng/L respectively.
Commencement Bay PAH concentrations in surface waters were slightly lower
than in Elliott Bay: 3.5 ug/g vs 5.0 ug/g. PCB and DDT, DDE and DDD
concentrations were all at or below detection limits.
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The major source of both dissolved and particulate metals was the
Puyallup River plume; whether from the river itself or entrained from
anthropogenic sources along the waterfront could not be determined.
Particulate metals increased with depth in the bottom nepheloid layer.
The low PAH concentrations on settling particulates in Commencement Bay
is consistent with low values on surface sediments in the deeper waters of
Commencement Bay found in other studies. The strong tidal currents prevent
their accumulation. Thus this bay behaves much like the northern end of the
main basin of Puget Sound.
1.1.6. Conclusions and Recommendations
It is quite clear that the dissolved contaminants, from whatever source,
remain in the very thin, fresh water plume and are transported through the
bays and into the main basin quite rapidly; roughly five days in Elliott Bay
and two days in Commencement Bay. The West Waterway is a source of high
concentrations of dissolved trace metals, but not as high as from the Denny
Way CSO and Harbor Island during periods of heavy rainfall. Because of its
limited duration this study could not determine the overall contribution of
the three principal sources in Elliott Bay on an annual basis. Observations
need to be made at the sources throughout a year. The sources for trace
metals in Commencement Bay appear to be much more diffuse, with no strong
point sources observed, although the industrial waterfront is strongly
implicated. Trace metal concentrations there were much lower than in Elliott
Bay.
It was not feasible to assess how much particulate material was deposited
directly at the mouth of each source. It would be difficult but not
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impossible Co do this in a monitoring program. The immediate deposition rate
is a major data gap. Directly beyond the sources, however, most of the
suspended particulate matter remained in suspension in the fresh water
plume. If a maximum of 4% was lost per day from the plume, approximately 80%
of the material would be exiting Elliott Bay after five days transit and 90%
would exit Commencement Bay after two days transit. The percentages are
probably higher than these. The losses from the fresh water plume would
affect particle-bound contaminants most significantly: toxic organics, lead
and chromium. The high source strengths of the West Waterway and the Denny
Way CSO were not unexpected. However, the runoff from the north end of Harbor
island during high rainfall was unanticipated but, in retrospect, not
surprising. It should be determined if the concentrations are a function of
ship-building activity.
PCB and DDT isomers were undetectable in Elliott Bay and Commencement Bay
water. Some PCB appears to be leaking into Elliott Bay, however. Extremely
high concentrations of PAH were measured near the Denny Way CSO and the
Duwamish West Waterway, which is substantiated by findings of high PAH
concentrations in the sediments at these locations.
There was no evidence that resuspension and transport of contaminated
bottom sediments was taking place in Elliott Bay. The presence of a
resuspended layer suggests that this does occur in Commencement Bay, but at a
very low rate.
This study strongly suggests that, just beyond the sources, most of the
contaminants entering these two bays enter the main basin quite rapidly.
There is virtually no resuspension of sediments in Elliott Bay and relatively
little in Commencement Bay, especially in water less than 100 m deep.
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Finally, it must be recognized that these studies took pLace over a
period of only a few days during two different months. The values measured or
calculated are probably "in the ball park" but the intermittent nature of
rainfall, runoff, and river flow require measurements over longer periods of
time to more accurately assess the total contributions of the various
sources. The contribution of diffuse runoff from waterfront sources is
ungauged and requires special attention.
1.2. INTRODUCTION
Elliott Bay and Commencement Bay are the two major commercial embayments
adjacent to the main basin of Puget Sound (Fig. I.I.). The bays are major
aspects of Puget Sound morphology, with horizontal dimensions of about
5x6 kms for Elliott Bay and 3x3 kms for Commencement Bay. Both embayments
are deep, 150-200 m, have steep sidewalls, and there are few areas less than
50 meters deep.
The waters of the bays are mixtures from two sources. The larger source
in volume is subsurface water from the main basin. The other source is the
freshwater discharge from the rivers entering the bays, which appears as a
relatively thin lens (a few meters thick at most) within the bays. Freshwater
discharges into Elliott Bay from the Duwamish River and into Commencement Bay
from the Puyallup River. Neither is a large river; the Puyallup is the fourth
largest river entering Puget Sound proper, with an average annual discharge of
3,756 ft3sec~l. The Green-Duwamish River is the sixth largest at
1,790 ft3sec_1. Maximum discharge of the Duwamish (which is controlled by
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Figure 1.1. Elliott Bay and Commencement Bay. Triangle marks the location of
the moored arrays.
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STRAITS of JUAN ds fUCA
NOAA-EPA	>
CONTAMINANT TRANSPORT STUDY
MARCH • JULY 1985
JANUARY 1986
!Y ISLAND'
ADMIRALTY INLET'
22'
: MAGNOLIA BLUFF
Elliott Bay
1ST POINT
ELLIOTT
SAY
-.DENNY WAY CSO
AUCI POINT
DUWAMISH HEAOc
WEST DUWAMISH WATERWAY
ijf EAST DUWAMISH WATERWAY
COMMENCEMENT
S^BAY
' \ POINT DEFIANCE
TACOMA NARROWS
Commencement
Bay
PUYALLUP RIVER—
I22"30' MIDDU WATERWAY
45'
30'

-------
dams on its tributaries) can be as high as 200 m3/sec primarily due to rain in
winter; the Puyallup can be as high as 500 m3/sec during snowmelt.
Prior to this study several investigations have focused specifically on
transport processes in Elliott Bay and the main basin of Puget Sound.
Transport studies in Elliott Bay have shown that pollutant-bearing particles
are added to the surface waters by river inflow, combined sewer outfalls,
atmospheric deposition, urban runoff, and other routes. Those particles that
remain suspended above the pycnocline are advected out of the bay by the
estuarine circulation (Sillcox et al., 1981; Baker et al., 1983). Particles
that rapidly settle out of the surface layer contribute to pollutant
accumulation in the bottom sediments. Bottom sediments may be a net sink for
particles rather than a source to the main basin (Baker et al., 1983), but no
quantitative information on the remobilization of bottom sediments by
resuspension at specific locations (such as disposal sites) was available.
Trace metal budgets constructed for Elliott Bay also suggest that, although
the bay is a sink for particles, it is a net exporter of pollutants
(Feely et al., 1983). For example, surface advection and tidal exchange carry
about 75% of the Mn input out of the bay. The enrichment of Pb, Cu, and Zn in
the hydrous Mn oxide phase on suspended particles suggests that pollutants
such as these are likewise lost from the bay to the same extent (Feely et al.,
1983; 1986).
This report includes data and information developed during 1985 and 1986
to determine how pollutants might be transported from Elliott Bay and
Commencement Bay (two of five EPA priority marine embayments in Puget Sound)
to the main basin of Puget Sound.
-14-

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1.3. GENERAL APPROACH
The Puget Sound Action Program, under Che direction of the U.S.
Environmental Protection Agency (EPA) and the Washington State Department of
Ecology (DOE), developed a budget initiative and a FY 85 Work Plan. The Plan
identified five priority marine embayments in Puget Sound as potential sources
of pollutants for the rest of the estuary: Elliott Bay, Commencement Bay,
Everett Harbor, Sinclair Inlet and Budd Inlet. The data presented here are
from a study that addressed the question of pollutant transport from Elliott
Bay in some detail and Commencement Bay to a lesser extent. There were four
study objectives:
•	obtain reliable, first-order estimates of the relative scale of each
transport path (surface plume vs. bottom nepheloid layer);
•	obtain information on the temporal variability within each path (e.g.,
is removal via the surface riverine plume predominated by a few winter
runoff events?);
•	determine the partitioning of pollutant contaminated sediments between
the transport paths;
•	identify the most profitable direction for obtaining quantitative
estimates of specific pollutant fluxes.
The general approach was to map the distribution of properties in the
water column (salinity, suspended particulate matter and toxic trace metals
and organics) using a large ship for sampling the subsurface water and a small
-15-

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boat to sample Che surface plume, which is only a few meters deep. One of the
sampling periods (January 1986) was chosen in an attempt to capture a combined
sewer overflow event in Elliott Bay (Unfortunately, the overflows are
unpredictable, occurring when the mains can no longer accommodate inflowing
water from heavy rainfall. An overflow event depends on the rate and location
of rainfall over the city.).
Current meters and sediment traps were deployed on a mooring in Elliott
Bay, to the south of the Pier 90 anchorage. A current meter was located in
the Ouwamish West Waterway (Fig. 1.1). The sediment traps were designed to
determine what proportion of the particulates in the surface plume is retained
in the bay.
In Commencement Bay two moorings with current meters were deployed in
late March in the center of the mouth of the bay. No sediment traps were
used.
II. RESULTS
II.1. ELLIOTT BAY
II.1.1 METEOROLOGICAL SETTING
Light rain (<0.1 inch/day) fell on April 2-April 5 during the 1985
sampling period. The highest sustained wind speeds at Sea-Tac Airport for the
period April 1-April 9 averaged 6.1 m/sec and varied between 4.5 and
8.0 m/sec. On the whole the winds were fairly light and constant in speed but
variable in direction.
Rainfall during the January 1986 sampling period was 0.21 inches/day for
January 8, 0.24 inches/day for January 9, and 0.08 inches/day for
-16-

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January 10. The winds during these three days were faster, more variable in
speed, and more constant in direction than for the previous April. The
highest sustained wind speed was 29 m/sec from the south on January 8. It
decreased to 4.0 m/sec from the southeast on January 9, and increased to
12.5 m/sec from the south on January 10.
II.1.2. Hydrographic Setting
Green-Duwamish River
The Green River flows 99 km from its source in the Cascade Mountains
through forest and agricultural land. Near Tukwila, it is joined by the Black
River, and is thereafter known as the Duwamish River. This combined river
system flows another 19 km through a heavily urbanized and industrialized
region to Elliott Bay (Puget Sound Task Force, 1970). The USGS monitors river
flow at several points along the Green-Duwamish River system. The highest
flows normally occur during December and January due to direct runoff of
rain. The winter flow usually decreases through March or April, followed by a
less pronounced peak in April, May, or June due to snowmelt runoff. The flow
values used in this report are those from the gauging station near Tukwila at
river kilometer 20. The Black River flow contribution downstream of this
gauging station is negligible (Santos and Stoner, 1972); so Green River flow
is assumed to equal that of the Duwamish River.
April 3-9, 1985
Mean monthly flow in April 1985 was 150% of the ten-year average for
April. During our sampling period, river flow was doubLe the ten-year average
for April (Fig. II.1). For the January sampling period the situation was
exactly reversed.
-17-

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Figure II.1. Discharge rates of the Duwamish River: ten-year average (1968-
1978) and monthly values (February 1985 - January 1986).
-18-

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DUWAMISH RIVER FLOW (Green River atTukwila)
200 n
10-YEAR AVERAGE
2 ISO
100-
| 50
i i Monthly Range (1968-1978)
X Monthly Standard Deviation
• Monthly Mean
200-1
$ 150
100 -
5 50-

m B
i	1	1	1	1	1	1	1	1	1	r
YEAR FEBRUARY 1985 - JANUARY 1986
(ZD Monthly Range (Feb 85 - Jan 86)
*	Monthly Mean
*	5 Day Sampling Period Mean
0
a
i r
FEB MAR APR MAY JUN JUL AUG SEP OCT NOV DEC JAN

-------
The unusually high flow rates at this time were a result of 17 days of
rain prior to our sampling dates. The freshwater flow of the Duwamish River
peaked at a daily average discharge rate of 130 m3/sec on the second day of
sampling (Fig. II.2) and decreased gradually to 55 m3/sec on April 9.
The Denny Way combined sewer overflow (CSO) had not discharged since a
storm on March 22-24.
January 8-10, 1986
Rainfall for the end of 1985 was much lower than usual. In December the
rainfall was 28% of the thirty-year monthly average. The January 1986 river
flow was 67% of the ten-year average for January and during our sampling
period was half the ten-year average (Fig. II.1). 1.85 inches of rain fell in
a storm which occurred December 31-January 5, but did not markedly increase
the river flow. The Duwamish River flow during our sampling period was
31 m3/sec.
This storm prior to our sampling period did, however, cause the Denny Way
CSO to discharge 23,000 m3 on January 3 and 42,800 m3 on January 5
(Fig. II.3). Six other CSOs also discharged during this storm. During the
overflow event sampled on January 8, 1986, the Denny CSO discharged a total of
16,800 m3 into Elliott Bay. The Harbor Island CSO also discharged 417 m3 into
the Duwamish River West Waterway several hours prior to our sampling. The
time history of the Denny overflow event is shown in Fig. II.4. Trace metal
samples SI through S12 and organic sample J1 were collected while the Denny
Way CSO was overflowing. Although the overflow events of early January are
significant, a much larger ('100-year') storm occurred later in the month, the
impact of which would be greater on the water quality of Elliott Bay than the
impact found in this study of a smaller CSO event.
-20-

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11.1,3. Physical Oceanography
Previous studies of currents focused on the middle water column to avoid
interference with moorings by shipping (Sillcox et al., 1981; Cannon and
Grigsby, 1980). Because those studies left an uncertainty in the magnitudes
and variability of flow in the very near surface and near bottom layers and in
the corresponding ability of those layers to transport particulate pollutants,
we made observations in those layers during spring through early summer
1985. The observations are summarized in Tables II.1-II.3 and various spatial
and temporal distributions are shown in Figs. II.2-II.13.
Observations were made in the northeastern portion of Elliott Bay using
surface and subsurface moorings of currents and water properties at 1, 4, 50,
98, and 101 m, in a water depth of 102 m (Table II.1). This location was
chosen because previous studies had shown that the surface plume from the
Duwamish River flowed along the north side of the bay and that potentially
erodable contaminated bottom sediments also existed on the north side near Che
Denny Way CSO. The moorings are at the base of the sloping bottom where the
bottom current gradients begin to decrease rapidly. Records from these meters
are nominally 114 days long starting in March.
In addition, a mooring to measure the variability in river discharge was
placed in the mouth of the West Duwamish Waterway, approximately 50 meters
east of the old fire boat station. An instrument was suspended at about 2 m
depth with a sediment trap immediately below in 10 m of water at mean lower
low water. Another meter was moored about 2 m above the bottom at the western
edge of the channel in water of approximately 15 m depth. The mooring was in
place from 27 March to about 12 June when it was struck and dragged to the
south end of the waterway, where it remained until August. Current records
-21-

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Figure II.2. Discharge of the Duwamish River measured at TukwiLa, Washington.
-22-

-------
I40-:
DUWAMISH RIVER DISCHARGE
26 March • 4 July, 1985
120 -
100 -
20-
I JUL
I MAY
IJUN
I APR

-------
Figure II.3. Discharge of the Denny Way CSO, January 3-5, 1986
-24-

-------
Discharge of Denny Way CSO
January 1986

3 5
8 10
15 16 18
22
27 30 Jan

-------
Figure II.4. Discharge of Denny Way CSO January 8, 1986.
-26-

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Discharge of Denny Way CSO
January 8,1986
O.IOn
Trace Metals Stations 1-12
Trace Organics Station JS
0.08-
0.06-
0.04-
0.02-
0.00
2:00 4:00 6:00
8:00 10:00 12:00 14:00 16:00
PACIFIC STANDARD TIME

-------
Table II. 1. MOORING LOCATIONS AND DEPLOYMENT DATES
Name	Location	Observation Depth	Duration
On)
PS8501
47-37-02N
122-22-42W
1
27
March

9 July



4
27
March
-
22 April



52
27
March
-
9 July
PS8502
47-37-06N
122-22-42W
98
27
March
-
9 July



101
27
March
-
9 July
PS8503
47-35-00N
122-21-34W
2
28
March
-
12 June



10
28
March
-
12 June
PS8504
47-17-42N
122-27-31W
1
25
March
-
15 April



4
25
March
-
15 April
PS8505
47-17-39N
122-27-15W
152
25
March
-
15 April
Table 11.2. CTD OBSERVATIONS
Date
No. Casts
Tide State
Location
27 March
14 casts
Higher High
EB
28 March
10 casts
Lower Low
EB
3 April
14 casts
Higher High
EB
4 April
3 casts
Lower Low
EB
2 July
23 casts
Lower Low
EB
25 March
7 casts
Higher High
CB
1 April
21 casts
Higher High
CB
15 April
11 casts
Ebb
CB
-28-

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from the surface meter proved to be unreliable due to a malfunctioning rotor
counter. Direction, temperature, salinity, and attenuation records, however,
appear to be reliable, as do all data from the bottom meter. Current data
from the bottom meter are limited to 27 March to 13 May when fouling of the
rotor occurred.
Water properties were measured throughout the bay on various tidal
conditions using a shipboard CTD (Table II.2). Some measurements were
conducted from the NOAA Ship MCARTHUR, a relatively large vessel, which
disturbed some of the thin surface layer prior to measurement (Fig. II.2) and
some were measured from a smaller launch (Fig. II.3). Means and variances
from the moored instruments are given in Table II.3.
II.1.3.1. Salinity
Salinity distributions are presented for the disturbed surface layer and
for the deeper water at 90 m (Fig. II.5). On March 28, the surface salinity
gradient is very steep near the Denny Way CSO. However, at high tide on
March 26, gradients are slight. The fresher water occurs along the eastern
shoreline, apparently moving counterclockwise around the bay. At low tide the
surface plume of freshwater flowed from the Duwamish to the right along the
eastern shoreline of the bay. In April, samples collected from the upper 2
meters of the water column exhibit the extremely thin nature of the surface
layer (Fig. II.3). Most of the freshwater is confined to the upper meter of
the water column. In July, during a period of very warm, calm weather and low
river runqff, observations from the launch also showed freshwater flowing
along the eastern side of the bay at low tide with salt water entering around
Duwamish Head at high tide (Fig. II.2). An area of higher salinity between
the east and west waterways of the Duwamish occurred during July, and another
-29-

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Table II.3. MOORED INSTRUMENT STATISTICS
Vector Total	Maximum
Mean Flow	Vector	Variance	Temperature Salinity
Depth	cm/sec	Variance	Axis	Mean Var Mean Var
Mooring m	@"True	(cm/sec)2	"True	°C	'/•«
EB
1(1)

*********

***
10.5
3.6
27.1
2.1

4(2)

3.0 @ 287
50.0
314
8.3
0.2
29.0
0.4

52(3)

*********
*****
***
8.8
0.8
29.8
0.1

98 0.8
e
270
24.9
m
8.5
0.5
30.0
0.1

101 0.8
0
239
16.7
264
8.4
0.5
30.2
0.0
D
2(4)

* i i i i_. i ¦ ¦ ¦
wTfTfTSnfwTfTfw
*****
***
8.5
0.2
28.3
0.6

10(5)

4.6 
-------
area of salcier water was seen off SeatCle near the Aquarium. Tidal currents
observed in the plume indicate that the freshwater couLd exit the bay in one
tidal cycle, and no water would be flowing from the Duwamish at high tide. It
appears likely that Duwamish River flow transits the bay in tidally-driven
pulses even during high river flow (See Section II.1.3.2., p. 39) At 90 m the
salinity is indicative of its source from the main basin, and much less
variability is seen. In March there was less than 0.1 parts per thousand
(ppt) variation in salinity within the bay. In July some structure is
apparent with higher salinity water entering around Duwamish Head. Salinity
sections from the Duwamish West Waterway in July showed little change at depth
between ebb and flood, while the surface variations range from a low salinity
of 22.5 ppt on ebb to 26.5 ppt on flood (Fig. II.4). The freshwater exits
during ebb and is driven up the estuary during flood. Within Elliott Bay the
freshwater lens enters from the Waterway on ebb, is pinched off on flood, and
then flows along the Seattle waterfront while more saline water is transported
up the estuary from Duwamish Head. This can account for some patchiness in
the salinity patterns within Elliott Bay, particularly if more than one tide
is required for the freshwater to transit the bay.
The CTD survey showed the salinity at the Elliott Bay mooring identical
to that recorded by the current meters (Fig. II.5). Also the salinity in the
waterway was low at low tide, and high at high tide; thus the salinity might
be correlated with tide stage. However, when the predicted tide series is
correlated with the current meter salinity records from either the Elliott Bay
or Duwamish moorings, there is nearly zero correlation. Since the upper meter
at 2 m in the Duwamish River is in the strongest part of the halocline, a
slight variation in vertical structure could lead to a large variation in
salinity. In Elliott Bay, where the fresher surface salinity must be advected
-31-

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Figure II.5. Elliott Bay salinity distributions for higher high tide (HHT)
and lower low tide (LLT), March and July 1985, near surface and 90 m measured
from the NOAA Ship MCARTHUR. The near surface CTD's are actually at a depth
of about 1 m. The following figure (Fig, II.6) shows the varying detail
possible in the upper 2 m. The location of the moorings, indicated by
triangles, are shown on the March LLT distribution only. Solid dots indicate
sampling stations.
-32-

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24'
122*22'
38'"
47"36'-

March 26,1985
• ||jl.?IER9l
I i ^<6?
Surface
Higher High Tide
V V • XL
\ \ >
r'^DENNY WAY CSO
\ \


• \_ 28.5
.. ¦
•
•

• AJ


DUWAMISH HEADsVjMW
WEST DUWAMISH WATERWAY
tli
J:
EAST DUWAMISH WATERWAY'
1 h-'

i -.u!

38'-
47°36'-
38'-
47°36'-
july 2,1985
'PIER 91	Surface
Higher High Tide
,OENNY WAY CSO
OUWAMISH HEAD?)
WEST OUWAMISH WATERWAY '
f EAST OUWAMISH WATERWAY.-
122 22
W 1-26.5
122 22
PIER 91
( 30.08 • lO.IAppt)
- 47°36'-
Mardt 26,198S
90m
.DENNY WAY CSO
- 47*36'
DUWAMISH HEADjkJtp ...a
¦	--n-'-ii t
WEST DUWAMISH WATERWAY*- fc;
f EAST DUWAMISH WATERWAY-
122 22
March 28, 1985
Surface
Lower Low Tide
PIER 91
-.DENNY WAY CSO
\ 8501
DUWAMISH HEADS
*18503
WEST DUWAMISH WATERWAY
EAST DUWAMISH WATERWAY
I
24'
122 22'
July 2.1985
Surbce
Lower Low Tide
PIER 91
DENNY WAY CSO
DUWAMISH HEAD;.
WEST DUWAMISH WATERWAY
EAST DUWAMISH WATERWAY
I
24'
i
122 22
July 2,1985
90 m
Ail Observations
PIER 91
.DENNY WAY CSO
DUWAMISH HEAD
WEST DUWAMISH WATERWAY
< EAST DUWAMISH WATERWAY.
- 47°36'-

-------
to the mooring from the Duwamish, the large variation in salinity in the upper
4 m indicates the patchy nature of the Duwamish discharge. The salinity
variations at 10 m in the Duwamish are a consequence of the source waters from
Elliott Bay. There are periods, approximately fortnightly, when a little
freshening occurs in the deeper water of the Duwamish, indicating possibly
greater mixing near the mouth of the West Waterway at those times.
The surface salinity in Elliott Bay frequently is lower than in the
Duwamish. The vertical salinity gradient at times is up to 6 ppt over a depth
of 9 m. There are also other times when the salinities at 1, 2, and 4 m are
nearly the same, and only 1 or 2 ppt different from the salinity at 90 m,
indicating the patchiness within the bay and the existence of mixing.
At depth the salinities in Elliott Bay were generally higher than those
at the same level in the main basin of Puget Sound off Shilshole probably
resulting from introduction from a deeper level (Baker et al., 1983).
Time series of salinity difference in the Duwamish and Elliott Bay
clearly demonstrate patchiness (Fig. II.9). Although the mean is about 2 ppt,
the series shows spikes of of 4-6 ppt indicating extreme vertical stability
within the patches. There are frequent thin freshwater lenses in the region
of the mooring. The scale and form of the patches are highly variable;
resulting from tidal forcing, variations in Duwamish outflow and wind
forcing. Between 16 and 18 April the salinity at both the surface and at 4 m
decreased significantly indicating a freshwater patch greater than 4 m
thick. For five days prior to this event the Duwamish was discharging at 100
cubic meters per second, a rate twice the average for the study period
(Fig. II.2). The winds over the Puget Sound region (Fig. 11.10) during the
discharge period were to the north which would tend to keep the freshwater
confined nearshore. Beginning on 15 April the winds shifted to the south
-34-

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driving the accumulated fresh water from the nearshore out into the bay. This
observation is an example of the strong effect the wind has on the location of
the patches. On ebb tide during the April CTD cruises, a rip line ran roughly
along the center of the bay from the mouth to the west waterway. At that time
the moorings were in the middle of the fresh side of the rip line. The effect
and significance of winds on transport are addressed in Sec. II.1.3.2.,
Currents (P. ). Details of wind effects would require many wind
observations within Elliott Bay at several points due to the complexity of the
shoreline, particularly the adjacent, tall buildings. However, it is clear
that the north-south alignment of the Duwamish valley and the Interbay valley
strongly direct the winds.
II.1.3.2. Currents
Current measurements were made near the bottom and surface in Elliott Bay
and near bottom in the Duwamish West Waterway (Fig. 11.11). The records near
the bottom in Elliott Bay extended over 100 days, but the record near the
bottom of the Duwamish was limited to 40 days due to fouling of the current
sensor by algal growth. The currents near the bottom were low, generally less
than 10 cm/sec, up waterway in the Duwamish and westward in the bay.
An indication of the slow bottom currents is clearly seen in the nature
of the sediments in the region of the measurements, which are fine silts and
clays. The mean near bottom speeds observed, 3.7 cm/sec in Elliott Bay and
6.2 cm/sec in the Duwamish, are quite low (Fig. 11.12). Near-bottom current
observations support the conclusion of Baker et al. (1983) that resuspension
of bottom sediment is negligible compared with the slow flux of fine sediment
coming into the lower layer of Elliott Bay from the Main Basin. The vector
mean flow (0.8 cm/s toward 239 T) (Table II.3.) measured at 1 m above the
-35-

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Figure II.6. Detailed salinity distribution in Elliott Bay over the upper 2 m
measured from a small launch. Sampling began at lower low tide and was
completed on higher high tide, 4 April 1985. Sample locations indicated where
samples were obtained for each specific level.
-36-

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26'	24'	22'	I22a2 OENNY WAY CSO
.OENNY WAY CSO

!*•
OUWAMISH HEAOVjMI
J&-
WEST OUWAMISH WATERWAY
¦ EACT OUWAMIM WATERWAY 1
OUWAMISH HEAO\r^i
A-
WEST OUWAMISH WATERWAY
^EAST OUWAMISH WATERWAY. ]
35'
L'
22'
39'-
0.50m
2.00m
kMAGNOUA BLUFF
MACNOUA BLUFF
«iL4 MILE ROCK
38*-
: MER 91
.OENNY WAY CSO
SivOOENNY WAY CSO
47*37'
36'
36'
OUWAMISH HEAD\i*4B
A-
WEST OUWAMISH WATERWAY |
; EAST OUWAMISH WATERWAY; •
OUWAMISH HEAbVi*4UI
WEST OUWAMISH WATERWAY:
. EAST OUWAMISH WATERWAY*:

-------
Figure II.7. Axial distribution of salinity along the Duwamish West Waterway
at lower low tide and higher high tide, 2 July 1985.
-38-

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DUWAMISH SALINITY SECTION
On
.§20-
I
t
Q 40
60
On
£ 20"
Q_
111
D 40
26 25 24 23
LOWER
LOW
TIDE
inn/niii/DhTT-Head °f
Mouth of Waterway Waterway
-4
- 2m
-0
H—7/2
7/3 GMT
Seattle Tide
HIGHER
HIGH
TIDE
17777777777777777777^^ Head of
Mouth of Waterway Waterway
60—1
I km

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Figure II.8. Time series of salinity measured at fixed Levels on the moorings
in Elliott Bay and in the Duwamish West Waterway. Salinity scales vary for
each instrument.
-40-

-------
30.0 q
25.0
20.0
30.01
28.0
26.0 J
^ 30.8
| 30.4;
£ 30.0
PS850I
Im ELLIOTT BAY
- 20.0
P 4*m°ELLIOTT BAY ¦>
r 30.0
28.0
L 26.0

PS8502
101m ELLIOTT BAY

30.8
:30.4
1130.0
PS8503
2m DUWAMISH

26 I	10
MAR APR
85

-------
Figure II.9. Time series of salinity difference. For Elliott Bay the
difference is between salinities at depths of 4 m and 1 m during April, and
for the Duwamish the difference is for 10 m and 2 m from April to July 1985.
-42-

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ELLIOTT BAY
4m - Im
i—i—¦—1—i—¦—¦—1—r
S 26	30 1 3
J"	Mar	Apr
£	85	85
D
E
z
-J 6 -|
<
«/» 4 -
DUWAMISH
I I l I I l l l l l l I
**¦
2 -
0 -
10m - 2m

6
R
I I i | I l i » i l » I l l I i I > i » i l l I | » l I i l l i i i I i l l » I l l I » l I i l I 1 l l l l l l I
i ¦ I i l i I I l I I I i l l l l l >
26 1
Mar Apr
85 85
10
20

10 20
"T
1
Jun
85
T
10
2
L0

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Figure 11.10. Vector time series of low pass filtered winds measured at Three
Tree Point, Puget Sound, located between Elliott Bay and Commencement Bay.
The vectors display the direction toward which the winds are blowing relative
to north.
-44-

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THREE TREE POINT WINDS
I . i i i I i i . i . . i i i . 1 ¦ . . . ¦ . i . i I.
15 i
0
15

25 1
Mar Apr
85 85
10
20
20	1	10	20	1
Jun	JuI
85	85

-------
-45-

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Figure 11.11. Time series of currents resoLved reLative to the approximate
bathymetry of the mooring sites. At the Elliott Bay mooring 300° T is along
bathymetry and 30" T is across bathymetry. The orientation of the Duwamish
West Waterway is along 0° T. Speed scales optimized for each record.
-46-

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ELLIOTT BAY
60 q 4m
I¦¦¦|¦<' ¦ ¦ ¦ < ¦ i ¦ | ¦ ¦ ¦ ¦i¦ ¦i¦ | iiii11 i i i | i i i i i i i i i | i i 11 i iiii | i i i11iii i | I I i I i i i i 11 ¦ ¦i i ¦ i i i i [ iii i 11 i i i | 11 i ii n n
26 I	10	20	I	10	20	I	10	20	I
MAR APR	MAY	JUN	JUL
85

-------
Figure 11.12. Histograms of near-bottom current speeds in the Duwamish West
Waterway and Elliott Bay.
-48-

-------
in
DUWAMISH - 10m
CM..
U
z
tli
2 *•
D
U
u
o
z *
LU
u
aC
LU
Q.
en"
Meon
6.
25
Mini mum
0.
00
Max 1 mum
17
.90
St-dev
3.
67
Var1 once
13
.45
Skewness
0.
52
Kur+os1s
2.
49
6.0 9.0
SPEED (cm/sec)
12.0
18.0
in.
ELLIOTT BAY - 101 m
(VI
LU
u
Z
Ui
o£
CC
D
U
U
o
I-
z
UJ
U
o£
LU
a.
on
Mean
3.
74
Mini mum
0.
00
Max 1 mum
14
. 32
St-dev
1.
86
Var1 once
3.
46
Skeuness
0.
65
Kur + os 1 s
4.
13

3.0 6.0 9.0
SPEED (cm/sec)
12.0
15.0
18.0

-------
bottom shows that the station Lies in the northern sector of the weak,
bathymetrically steered counterclockwise gyre observed in the bay. Currents
in excess of 6 cm/s occurred less than eight percent of the time
(Fig. 11.12.}. The suspended sediment concentration varies directLy with
salinity with time, indicating that the suspended sediment is being carried to
the site by the currents rather than being resuspended locally (Fig. 11.23).
Because Elliott Bay is a quiet embayment with a deep entrance, the suspended
sediment and water properties below the surface layer have essentially the
same vertical distributions as those outside the entrance in the main basin.
Tidal currents at the bottom of Elliott Bay are very small, 1.5 cm/sec
and 0.8 cm/sec for the semidiurnal and diurnal components, with major axis
orientation along 93°. The surface record was too short to perform a complete
tidal analysis. Spectral analysis, however, showed more energetic currents
with a peak in variance in the semidiurnal range. The mean speed was an order
of magnitude greater than at depth.
The low frequency data (35 hour low-pass filtered to remove the tidal
signals) display an event-dominated environment (Fig. 11.13). At depth the
Larger magnitude vectors tend to align with the local bathymetry. There are
periods of reversal of flow into Elliott Bay, but these are infrequent and of
short duration. The magnitude of the low frequency flow is up to 20-30 cm/sec
in the surface but less than 5 and 3 cm/sec, respectively, in the two near
bottom records. The decrease near bottom most Likely results from the deepest
meter being in the bottom boundary layer since the meter is only 1 m off the
bottom.
Progressive vector diagrams of the Elliott Bay current records are more
instructive of the low frequency flow (Fig. 11.14). These are created by
putting successive vector currents at a given location end to end to give an
-50-

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overall impression of the flow. However, because they are from the
same location, they should not be interpreted as trajectories. The net flow
near surface is westward, out of Elliott Bay. The diagram reveals that the
flow is not steady, but is episodic in nature with periods of well-defined
flow in directions other than westward, including toward shore, and there are
periods of little or no defined flow. At depth, periods of weak, net flow
occur in early April and late May. A large change in direction (-45°) of flow
occurred between 98 and 101 m and is not presently understood. The net flows
imply a potential flow out of the bay in about 5 days in the surface layer and
14 days at depth. However, the direction of flow at the nearest bottom meter
implies flow more nearly across the bay, perhaps toward Duwamish Head, but of
course the flow may change direction farther on. The cross-bay flow would be
somewhat surprising because it was anticipated that the net bottom flow would
be more into the bay. Perhaps there is more inward flow at depth on the south
side of the bay.
II.1.4. Particulate Matter Transport
The purpose of this portion of the study was to examine the nature and
extent of the SPM surface plume in Elliott Bay during varying river flow and
runoff conditions. Specifically, it will characterize the SPM plume in terms
of its principal sources, extent, suspended load, vertical flux, and
trajectory.
An understanding of the distribution of suspended particulate matter
(SPM) in Elliott Bay is of fundamental importance to understanding related
pollution problems, since most pollutants are in particulate form or absorbed
to particles. The SPM distribution in Elliott Bay was characterized by Baker
et al. (1983) as a thin (<5 m), turbid, surface layer and a thicker (10-100 m)
-51-

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Figure 11.13. Vector time series of low frequency currents at the Elliott Bay
mooring oriented relative to 300" T, along the local bathymetry. The scales
of magnitude of the vectors of each record are different because of the varied
ranges of currents.
-52-

-------
300	1111111111111 ¦ 				
c"* 1
UJ
Q.
to
tn
N
Li
-30
4m
\(4
V 4Vk ..*.1 -

I
N
5*
}¦
300

4 i
UJ
in
UJ
cn
98m
I	
o

300

2.5 n
UJ
tn
in
o

I0lm
XAv,^ _>L
j^nr
111 ¦ 1111111 ¦ 11111 ¦ 11111111111111111 [ 11111111111111111111M111111111111111 ¦ 1111 ¦ 1111111111 ¦ 11111111111
26 I	10	20	I	10	20	I	10	20	I

TW;f»f
4
0
L-4
2.5
0
- -2.5
MAR APR
85
MAY
JUN
JUL

-------
Figure 11.14. Progressive vector diagrams o£ currents in Elliott Bay. The
record at 4 m is only 26 days long, which indicates the higher velocities than
at depth.
-54-

-------
26 DAYS
-40 -20
K t I owe+er#
20 40



Win
114 DAYS
£



f







'-00
-40 -20
KI Ionflters
20	40
114 DAYS
-40 -20
KI Io««tora
20	40

-------
benthic nepheLoid layer (BNL) separated by a zone of uniform and low SPM
concentrations. That study showed that the surface pLume was restricted to
the eastern inner bay and northern outer bay during August 1979 and February
1980 surveys. In a related study, Baker (1982) estimated that during a twelve
day period, the Duwatnish River supplied -214 x 10s g of the 298 x 10s g
suspended load of the inner bay freshwater plume. Another plume source, the
Denny Way CSO, discharged 850 x 10s g of suspended solids into Elliott Bay
from March 3, 1978 to February 28, 1979 (Tomlinson et al., 1980).
The stations/grids sampled are shown in Figs. 11.15 and 11.16 (1985 and
1986 surveys, respectively). Surface parameters measured in 1985 with the
respective sampling locations are listed in Appendix XVI. A discussion of
methods and instrumentation is in the Quality Assurance Project Report
(Appendix XVII) (also see Baker and Milburn, 1983).
It should be noted that the SPM values reported in this section are
derived from calibration regressions (see Appendix XVII). Since these
correlations contain a degree of scatter, a slight disparity may occur between
discreet sample SPM concentrations and corresponding values derived from
attenuation. Scatter about the regression lines is from sampling error and
particle population inhomogeneity. A persistent sampling problem is that of
obtaining attenuation and discreet measurements on downcasts and upcasts
respectively, i.e. they are not coupled in time and space. Errors associated
with particle population inhomogeneity have been discussed by Baker and
Lavelle (1985).
Plan view and vertical cross sectional maps of SPM and salinity
concentrations were constructed to depict the distributional patterns.
-56-

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II.1.4.1. April, 1985
(Note that in the vertical sections that the upper 2.5 m is shown
separately in expanded scale and that the shallowest measurements of the full
sections begin at 5 m).
The general distribution of SFM in Elliott Bay measured during the 1985
survey was similar to that described by Baker et aim (1983). The highest
concentrations were in the surface plume and BNL with uniform low turbidity
water throughout the water column between the two layers.
The surface plume is well defined by both SFM and salinity gradients and
its three dimensional extent throughout the bay is readily identified from the
vertical (Figs. II. 17, 11.18) and areal (Figs. 11.21., 11.22) plots. Surface
plume SPM concentrations ranged from ~10 mg/L at the West Waterway to
-1.0 mg/L in the central outer bay (Fig. 11.20, Section C-C'). Section line
A-A' (Figs. 11.16) shows that the plume diminished rapidly with depth (from
10.0 to 2.0 mg/L within 2 m) at the West Waterway but only gradually with
distance from the West Waterway. Section lines B-B' and C-C1 show that the
plume is constrained to the northern half of the bay. SPM concentrations in
the northwest quadrant of the bay ranged from -1 to 3 mg/L. Section line D-D'
shows that the plume, well defined along the eastern shore (1.5 to 5 mg/L in
the upper 1.5 m) diminishes gradually toward mid-bay where it is reduced in
thickness (<0.5 m) and concentrations (1.5 mg/L). Section line E-E' which
extends around the perimeter of the bay, shows relatively high concentrations
from the West Waterway (10 mg/L) to the Bay's confluence with the main basin
of Puget Sound (-1 to 3 mg/L). In general, the SPM concentrations around the
Bay perimeter decreased gradually in a counterclockwise direction. The
1.5 mg/L isopleth, which tends to delineate the lower boundary of the plume at
-1.5 m depth, truncates west of the West Waterway. High SPM concentrations
-57-

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Figure 11.15. Station locations in Elliott Bay during April, 1985 (a) and
January, 1986 (b). For April, 1985 (a), the names for stations sampled from
the McArthur (squares with bold italic numbering) are derived by adding the
prefix 'EB85-' to the station number. Names for stations sampled by small
boat (dots) are derived by adding the prefix 'EB85-SB' to the station
number. For January, 1986 (b), names for samples collected by small boat are
derived by adding the prefix *S' to the station number.
-58-

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a
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April 4-5.190S
MAGNOLIA BLUFF
4 MILE ROCK
PIER 91
.DENNY WAY CSO
DUWAMISH HEAO\i!-Ull
WEST DUWAMISH WATERWAY
EAST DUWAMISH WATERWAY
b
I22°20'
47*37'-
NOAA-EPA
Contaminant Transport Study
L-RERP 86-1
january 8-9.1986
• • (magnolia BLUFF
4 MILE ROCK
JAN 8,1986 /
PIER 91	/
y ''jAN 9,1986
•6 % -DENNY WAY CSO
V
3 / - 44 -43
40t42
• * 24 2S 24
X3.4-32 * . 'A*.
DUWAMISH HEAD-
X-
WEST DUWAMISH WATERWAY
EAST DUWAMISH WATERWAY

-------
Figure 11.16 Location of transects sampled for SPM and salinity in Elliott
Bay, April 1985 and January 1986. Data from these transects were used to
construct vertical contours of SPM and salinity.
-60-

-------
NOAA-EPA
Contaminant Trantport Study
L-RERP 85-2
April 4-5.1985
MAGNOLIA 8LUFF
i MILE ROCK
VI. DENNY WAY CSO
C DUWAMISH HEAO^J^JII
jilt-'*-
WEST DUWAMISH WATERWAY:
EAST OUWAMISH WATERWAY
Section lines for vertical cross sections
April 1985
24'
22'
NOAA-EPA
Contaminant Transport Study
L-RERP 86-1
January 8-9,1986
MAGNOLIA BLUFF
MILE ROCK
38*
PIER 91
.DENNY WAY CSO
•DJ
OUWAMISH HEAD
WEST OUWAMISH WATERWAY!
EAST OUWAMISH WATERWAY-
Section lines for vertical cross sections
January 1986

-------
Figure 11.17. Vertical sections of SPM in Elliott Bay, April 4-5, 1985.
-62-

-------
I? ?
SgE
ti S Ia o U 3
_i	i	i	i	i m
|
I
5"
m _
|2
JF h
- EB85-SBT14
EB6S-SBI4
EBoS-SBDI
EooS-Sa/
Danny Way CSO
-EE8SSB6
- EMS-SB2
EB8S-SEI
EBas-sen
W. Wiuiwty
- EB85-SB3
EB85-SBTI
EB85-SBT4
EB65-S68
S S

a
IMS-ftM
tMMtlt
eets-stTt

CB8S-I) O '
/
EUS-SBTB
EMS-SBI3
/
EB8S-SB9
EB8S-$8T6
EBSSSdS
EBBS-SB)
CD
CD
- EB8S -S6T1I
- EB6S-SBTS
- EB65-SB8
CD

-------
Figure 11.18. Vertical sections of salinity in Elliott Bay, April 4-5, 1985.
-64-

-------
e e c s e 3
¦ »
I"?
IgS
i
a.
I
® —
$5
EB8SSBI4
6B85-S8T12
DuttyWtyCSO
MS-SB7
EB8SSB2
K. Wtttrwiv
S8Tj
- EBas-sen
W. Watuwiy
EM5-SB3
EB85-SBT1
- EB6SSBT4
-EB8S-S68
SSsHSssui
—i	t j q
w
itiisitui
I
EBK-t)
CbL
* * I K
jJV EMS-SBT8
0
/
If ¦
I
EMS-SBt
EBB-SBT6
g S 3
IBW-S

s

EB8S-SBT5
EB6S-SB8

-------
Figure 11.19. Vertical sections of SPM and salinity in Elliott Bay,
January 8-9, 1986.
-66-

-------
C' 3
a L4 ?«
ac
-u
* J „s
^ w «n
* a a
St SI K
i 38 1*
L-RERP 86-1
January 8-9, 1986	line D-D'
a)	Vertical distribution of SPM (mg/l)
b)	Salinity (ppt) in Elliott Bay

-------
Figure 11.20. Near-surface SPM 0-2 m in Elliott Bay, April 4, 1985.
-68-

-------
12'
0 m
[HAGNOUA M.UH
V 4 HUE ROCK
i^DtNNT WATCSO
4.0 •
£0
OUWAWSH HEADAj««4Ul
Jt'-
WIT DUWAWSM WATERWAY
^ cast OUWAHBH WATERWAY
I
0.25 m
f HAGNOUA WW
V«wj*ock
10
j^QENNY WAY GO
OUWAHBH MIAO\|/®*i
wfjr ouwamsh waterway
^*EAST OUWAHtSH WATERWAY
J.
I
0.50 m
[hacnouasuiw
V 4 Mlf ROOC
>MMNY WAY CSO
a.o
OUWAHBH HCAOVjpUl
4	-9.01
WEST DUWAMtSM WATERWAY \
*EAST OUWAHISH WATERWAY'
1.0 m
[MAGNOLIA ALU PP
; PIER 91
>OENNYWAYCSO
mjWAHtSH NCAO\1/44i
T*5.0
WEST OUWAHtSM WATERWAY!
EAST DUWAPVSH WATERWAY }
1.5 m
•>QENMYWAYCSQ
10
OUWAHBH HIAIMLJ^UI
A:- ¦	^ i
WEST OUWAHBH WATERWAY1
EAST DUWAM1SH WATERWAY
X
2.0 m
[hagnoua aujfr
>OENNYWAYCSO
<1.0
^*MSM ^$o!
wijrouwAmM waterway
WATERWAY
Near-Surface Concentrations
ofSPM (mg/l)
Elliott Bay
April 4,1985

-------
Figure 11.21. Concentration of SPM in near surface of Elliott Bay
January 8-9, 1986.
-70-

-------
26'
24'
22'
I22°20'
39'-
NOAA-EPA
Contaminant Transport Study
L-RERP 86-1
January 8-9,1986
38'-
47°37'-i
^DENNY WAY CSO
36
36'"
35'-
MAGNOLIA BLUFF
4 MILE ROCK
PIER 91
Surface
Total Suspended
Matter
(mg/L)
DUWAMISH HEAD;
WEST DUWAMISH WATERWAY h
C^EAST DUWAMISH WATERWAY

-------
Figure 11.22. Near surface salinity in Elliott Bay, January 8-9, 1986.
-72-

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26'
39'-
38'-
47°37'-
36'-
35'-
• •
DENNY WAY CSO
MAGNOLIA BLUFF
MILE ROCK
V i
PIER 91
122° 20'
NOAA-EPA
Contaminant Transport Study
L-RERP 86-1
January 8-9,1986
Surface Salinity (ppt) *
Elliott Bay
January 8-9, 1986
DUWAMISH HEADS
WEST DUWAMISH WATERWAY
EAST DUWAMISH WATERWAY

-------
Figure 11.23. Salinity-SPM regressions in Elliott Bay.
A.	Surface - April 1985,
B.	Intermediate depths - April 1985
C.	Surface - January 1986
-74-

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• >Sm
	I.22X - Ji.OIr* = 0.48
5.0-
1.8-
4.0-
1.4-
3.0-
1.0-
2.0-
0 6-
1.0
o Bay Water
	-0.IISX-t-l0.3r2 =0.52
• Duwamish Stations S2I-S24
	-0.I67X-1-6.73i1 =0.94
•: it:-' ••
	1	1	1	1
29.6 29.8 30.0 30.2 30.4 30.6
0.0
0.2
20 25 30 35
5
10
15
10-
_i
E
• >21ppt Salinity
O <22ppt Salinity
—	-0.330X + lO.Or1 = 0.80
—	-0.617X + I6.7i* = 0.94
25
30
5
10
15
20
SALINITY (g/kg)	SALINITY (g/kg)	SALINITY (g/kg)

-------
were also found at the East Waterway (8 mg/L), along the easternmost shore
(5 mg/L) and about halfway between the Denny Way CSO and Pier 91. It appears
that these high levels decrease to background plume concentrations (-2 mg/L)
within a relatively short distance (several hundred meters).
The BNL SPM concentrations ranged from -1.5 mg/L in the central outer bay
to -0.5 mg/L in the inner bay. Intermediate water SPM concentrations were
relatively uniform (0.4-0.6 mg/L) throughout the bay (Fig. 11.17).
II.1.4.2. January 1986
The patterns of SPM and salinity measured in January, 1986 was similar to
those observed in 1985 but the concentrations were much lower and higher,
respectively. Plume concentrations ranged from -1-10 mg/L in the upper 3 m in
the West Waterway decreasing in both magnitude and thickness from mid-inner
bay to the northeast shore (Fig. 11.19, Section A-A). In the outer bay,
concentrations were less than 2 mg/L along the entire B-B1 line. Section C-C'
shows that SPM concentrations in the upper 2 m decreased from a high of
7.5 mg/L at the eastern end of the bay to -1 mg/L at mid-bay. Shoreline SPM
concentrations are dramatically reduced from the 1985 survey except at the
West Waterway. The slight elevation in concentration near station S34 may be
from the Fairmount CSO and nearby storm drains.
The near-surface salinity patterns (Fig. 11.21) matched the SPM patterns
(Fig. 11.22) with some exceptions. The mid-outer bay plume is not discernable
from the salinity measurement but is apparent from the SPM measurements. In
section D-D* (Fig. 11.18) there appears to be a secondary but well-defined low
salinity plume to the west of the West Waterway slightly offshore of the
Fairmount CSO (station S34). The nearshore plume is much better defined by
the salinity than the SPM measurements, especially at the East Waterway.
-76-

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The foregoing results and those of Baker (1982) show that the primary
source of the SPM load of the surface plume in Elliott Bay is the West
Waterway of the Duwamish River; secondary sources were shown to include the
Denny Way CSO, East Waterway and the Fairmount CSO. The difference in
magnitude of the plume SPM concentrations between the two surveys reflects the
changes of the Duwamish discharge. The Denny Way CSO discharge, although
relatively minor in volume, made a significant contribution to the plume
suspended load in the northeast quadrant of the bay during the 1986 survey.
The extent of the plume was well defined by the SPM and salinity
distributions and was found to be similar during both surveys. It was
primarily located in the southeast and northwest quadrant of the bay and
decreased in intensity from its source in the southeast quadrant to the
northwest quadrant, and from the bay shoreline to the center. In general, the
plume was thickest (-2-3 m) at the shoreline and thinned (to -0.5-1 m) toward
the center of the Bay.
The SPM and salinity distributions indicate that the plume spreads
outwards from the Duwamish River in a thin, low salinity lens. The plume is
transported counterclockwise throughout the bay, until it is carried into the
main basin off Magnolia Bluff.
II.1.4.3. SPM-Salinity Relationships
The distribution and fate of SPM from the Duwamish Waterway is governed
by processes such as advection, settling and dilution. An examination of the
relationship between SPM concentrations and salinity provides some clues about
the relative importance of these processes.
The 1985 surface salinity distributions in water less than 5 m clearly
mimic SPM surface patterns (Figs. II.3. and 11.19) suggesting that dilution of
-77-

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the river plume by marine water from the main basin was the major factor
controlling the decrease of SPM concentrations in the bay. Least-squares fits
to the salinity data greater than and less than 22 ppt produced separate
regression lines with high correlations (r2 = 0.80 and 0.94) (Fig. II.23a).
These correlations imply that plume SPM behaves conservatively and that its
distribution within the surface plume is governed by simple physical mixing
(dilution) (Liss, 1976). Furthermore, the fact that two linear mixing curves
can be fit to the data set implies that secondary sources mix with the
Duwamish water. The linearity of the mixing curves argues that SPM loss (by
settling or other processes) is insignificant.
The January 1986 surface SPM-salinity regression (Fig. II.3c) is
considerably different from that of April 1985 (Fig. II.23a). Duwamish water
(stations S21-S24) exhibited conservative mixing from station S24 riverward
and into the West Waterway. The bay water SPM-salinity relationship is
clearly different from that of the riverwater. It shows a linear trend with a
steeper slope and a low correlation coefficient (r2 = .48). It is possible
that the scatter of the data is a result of multiple sources (Denny Way,
Fairmount, and Hanford CSOs and waterfront runoff); the survey followed a
period of moderate to heavy rainfall (see discussion on CSO discharge).
The SPM-salinity relationship within waters beneath the plume was the
inverse of the plume water relationship (Fig. II.23b) and was qualitatively
similar to those reported by Baker et al, (1983). Slopes differ between the
present study and Baker et al. (1983) because midwater and bottom water
samples were plotted in this study whereas only BNL samples were used by Baker
et al, (1983). The direct relationship between SPM and salinity in the deep
water indicates that the increased turbidity of the deep water is caused by
advection of Main Basin deep-water rather than local resuspension.
-78-

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II.1.4.4. SPM Loading and Vertical Mass Flux
The mass loading of Che upper 2 m of Elliott Bay was estimated by the
following procedure. First, attenuation measurements obtained at each station
at several depths (0 m, 0.2S m, 0.50 m, 1.0 m, 1.5 m, and 2.0 m) were
contoured. A separate contour map was constructed for each depth level. The
area within each contour interval on each depth level was measured with a
polar planimeter and the loadings of the subareas (contour intervals)
calculated by
z s depth increment (m)
a = area of subarea (km2)
The Lg values were summed to provide the loading of each depth increment
and then successively deeper depth increment Loadings were averaged and
summed:
L ¦ (a ~ *34) za*106
s	.74
(Eq. II.2)
where Lg 3 loading (g) of each subarea
(——= coefficients of the attenuation(a)/SPM regression
(Eq. II.3)
and
i=6
L
P
L.
l
where
(Eq. II.4)
i=0
-79-

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= loading of a depth increment
L_ = loading of upper depth increment
Lz+£ = loading of lower depth increment.
The calculated loadings are given in Table II.4
Nearly half of the material was in the upper half meter. Thirty percent
was in the next half meter. Only 22.3% was in the second meter.
The average vertical mass flux, from sediment trap data from mooring
PS8501 (Table II.5), was calculated to be 0.155 g/m2/day at both 6 m and 50 m
depth. Multiplying the flux by the area of the plume (13.5 km2) gives the
vertical mass flux of the plume as 29.9 x 10s g/day, assuming that the flux at
mooring PS8501 is representative of the entire plume area. This is 4% of the
total mass loading of the 2 m deep plume. This small loss would not be
revealed in the regression of SPM and salinity (Fig. 11.23). Moreover, this
is a maximum figure, since the vertical flux should be proportional to the
mass loading at any given point and the mooring was located in the region of
maximum mass loading. A more likely value would be 2.5%.
II.1.5. Trace Metals and Organics in Elliott Bay
II.1.5.1. Trace Metals
Dissolved and particulate trace metal samples were collected in Elliott
Bay on 4-5 April, 1985 (Fig. 11.24), during a period of moderate to high river
runoff when the combined sewer overflows were not discharging. Surface trace
metal samples were collected in 1-L polyethylene bottles from the bow of a
small boat deployed from the NOAA ship McArthur while subsurface samples were
collected using Go-Flo bottles attached to Kevlar line or hydrowire.
Additional trace metal samples were collected in Elliott Bay on 8-10 January
-80-

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Table II.4. Mass loading of the upper 2.0 m of Elliott Bay.
Depth Mass %
Increment	x 1QS g	of total
0
m -
.25
m
169.0
20.2

.25
m -
.50
m
233.2
27.9

.50
m -
1.0
m
247.6
29.6

1.0
m -
1.5
m
126.7
15.2

1.5
m -
2.0
m
59.5
7.1
Z = 836 x 105 g
Table II.5. Vertical mass flux at 6 m and 50 m at mooring PS8501 during the
April, 1985 survey.
Cylinder No. - Hours of Collection	Mass Flux (g/m2/day)


6 m
50 m
1
204
.09
0.11
2
204
.10
0.14
3
204
.14
0.15
4
204
.10
0.14
5
204
.23
0.21
6
204
.27
0.12
7
204
.14
0.10
8
204
.24
0.26
9
204
.11
0.11
10
204
.13
0.21


x = 0.155
x = 0.155
-81-

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Figure 11.24. Stations and location of vertical transect for metal sampling
in Elliott Bay.
-82-

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39'-
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April 4-5,1985
MAGNOLIA BLUFF
4 MILE ROCK
38'-
PIER9I
DENNY WAY CSO
DUWAMISH HEAD
DRO
/ _
WEST DUWAMISH WATERWAY
: EAST DUWAMISH WATERWAY;
!.*•»

-------
-83-

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1986 from small boats. During early January 1986, a period of relatively high
rainfall (7 inches in 14 days) caused numerous overflows of the combined
sewers to discharge into Elliott Bay. The Denny Way CSO was discharging for a
period of 12 hours prior to the sampling program.
Surface samples collected throughout Elliott Bay (Figs. II.26-11.39) were
used to look for sources of trace metals to the bay. Near a source, a plume
of water with high metal concentrations will be evident with concentrations
decreasing as the plume is diluted with more saline water. Plumes in Elliott
Bay which contain high concentrations of trace metals originate from the East
and West Duwamish Waterways, the Harbor Island shipyards, Denny Way CSO and
the Seattle waterfront. Although a single concentration in a given plume can
not be used to precisely calculate trace metal fluxes, the concentration
within a plume can be used to perform an order-of-magnitude estimate of the
flux of contaminants if flow data are available. Areal distributions for each
metal have been contoured for both the April, 1985 and January, 1986 data
sets. In addition, vertical transects (Fig. 11.24) were generated from the
deep samples collected in April 1985. These transects show that the surface
plume which contains high concentrations of metals is confined to a very thin
layer of surface water (<10 m). The salinity measurements provide a better
definition of the thickness of the plume because of their higher vertical
resolution. These vertical transects can also be used to identify sub-surface
sources of metals such as diffusion from the sediments.
Trace metal-salinity plots were used to estimate "apparent river
concentrations" which were then multiplied by the freshwater flow to calculate
the flux of metals out of the Duwamish Waterway and out of Elliott Bay. After
individual plumes merge together, the water from these plumes will exhibit
characteristics of a single water mass and mix en masse with more saline
-84-

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water. If the metal is conservative, a plot of trace metal concentration vs.
salinity will reveal a straight line between the single mixed water mass and
more marine seawater. Boyle et al. (1974) have shown that the flux of a
conservative element passing an iso-haline is equal to:
Qr [C - (S-Sr)*dC/dS](Eq. II.5)
where Qr and Sr are the flow and salinity of the river, respectively and
where C and S are the concentration of the element and salinity at the
iso-haline, respectively.
If the measurement of flow was made in freshwater, then Sr is equal to 0.0 and
Qr becomes the flow of freshwater. In this case, the part of the eq. II.5 in
brackets is the y-intercept of a straight line. Fig. 11.25 shows examples of
idealized mixing curves for conservative trace metals from various sources.
If plumes from different sources merge in the freshwater portion of the river,
the line would be linear throughout the entire salinity range and the
y-intercept would be the concentration of mixed river endmember (solid line in
Fig. 11.25). However, if there is an additional input of metals at some
higher salinity, the curve would have a metal concentration-salinity plot
which is convex upward (dotted line in Fig. 11.25). After the plume has mixed
laterally across the river plume, the mixture will again exhibit a linear
metal-concentration vs. salinity plot. In this case, the y-intercept or
"apparent river concentration" for the line segment seaward of the salinity of
complete lateral mixing will be higher, reflecting the additional input. The
portion of the metal concentration-salinity plot seaward of the salinity of
-85-

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Figure 11.25. Hypothetical Example of trace metal transport for a river with
flow of 1 m3/sec. Conservative mixing when river concentration is 2 ug/L
which results in a transport of 2 mg/sec (	). Conservative mixing when
river concentration is 2 pg/L and 8 mg/sec is discharged at 10 g/kg salinity
(0). In this case, the total transport of metal is equal to 10 mg/sec.
Conservative mixing when river transport is 10 mg/sec with no additional input
at higher salinity, i.e. river concentration is 10 ug/L (	). In all cases,
the seawater concentration is 0.1 ug/L.
-86-

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10
9
8
7
6
5
4
3
2
I
0
v.
•••
2 4 6 8 10 12 14 16 18 20 22 24 26 28
SALINITY (g/kg)

-------
complete lateral mixing would be identical to a line in which the same flux of
metal originated entirely from the river with no additional sources being
added at higher salinity (dashed line in Fig. 11.25). In terms of eq. II.5,
the flux of trace metals across the iso-haline of complete lateral mixing
would be the same for both cases (dotted and dashed lines) since the same
amount of metal was added upstream of the iso-haline. Plots of trace metals
vs. salinity were generated for Elliott Bay data in April 1985 and January
1986. A linear regression analysis was performed on those samples that were
1) more saline than the inferred iso-haline of lateral mixing (14 g/kg for
April 1985 and 24 g/kg for January 1986; and 2) not part of an observed
plume. For particulates, only samples that were taken on the day of the
overflow event were used in regression analysis for transport out of the
bay. If the r2 of the linear regression was greater than 0.5, the y-interceptf
of the regression was multiplied by the average freshwater flow to calculate
the flux of metals out of Elliott Bay. A linear line segment seaward of the
salinity of complete lateral mixing does not demonstrate complete conservative
behavior of a trace metal. Dissolved trace metals can be lost from solution
during lateral mixing or on a time scale longer than estuarine mixing. The
dissolved and particulate trace metal may also be non-conservative to an
extent less than the errors of the regression analysis. Temporal variability
of the discharge of a conservative trace metal can also result in a deflection
in a trace metal-salinity plot. Results from the four samples collected from
the West Duwamish Waterway were used to calculate the transport of metals out
of the West Waterway. By comparing the transport of metals out of the West
Duwamish Waterway with the transport of metals out of Elliott Bay, the
combined significance of the plumes from the East Duwamish Waterway, the
Harbor Island shipyards, the Denny Way CSO and the Seattle waterfront can be
assessed.
-88-

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Aluminum
Since most of Che aluminum in marine particulate matter occurs as
aluminosilicate (Sackett and Arrhenius, 1962), the A1 concentrations in the
suspended matter can be used to estimate the aluminosilicate percentages in
the suspended matter (A1 x 12). Moreover, the Al/trace metal ratio can reveal
if the metal sources are other than normal geological (sediment) ones, since
aluminum is not normally a contaminant. The variations of the distributions
of particulate A1 in Elliott Bay are due to seasonal changes in input of
suspended materials into surface waters and variations in bottom currents in
Puget Sound which effect the resuspension and transport of bottom sediments
into the bay. The highest concentrations of particulate A1 in surface waters
(250-850 mg/L), originate from the Duwamish River and the Denny Way CSO
(Fig. 11.26). Al-rich particulate matter is observed in the northern half of
the bay and outward into the main basin of Puget Sound, providing evidence for
out-of-bay transport of aluminosilicate material in near-surface waters.
Below the surface, particulate AL concentrations decreased to a minimum at
20-40 meters followed by a gradual increase to the bottom. The increase in
concentration of aluminosilicate materials in near-bottom waters is probably
the result of advective transport of material into the bay from the main basin
since the bottom currents are too slow to resuspend bottom sediments
(Section 11.1.3.1.).
Iron
In both April 1985 and January 1986, plumes of dissolved Fe originating
from the West Duwamish Waterway and the Seattle waterfront can be seen
(Figs. II.27a-b). In January 1986, an additional plume can be seen
-89-

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Figure 11.26. Surface distribution of particulate A1 in Elliott Bay during
April 1985 (a) and January 1986 (b). Particulate A1 vs. salinity plots for
April 1985 (c) and January 1986 (d). Results of regression analysis of
samples in Elliott Bay are presented as solid lines. Samples in the plumes of
the West Duwamish Waterway (WW) and the Denny Way CSO (CSO) are noted as open
circles and are not used in the regression analysis. For the January 1986
regression, only samples collected on the day that the CSO discharged were
used in the regression analysis. A regression of the samples collected in the
West Duwamish Waterway is presented as a dashed line (-—). In the vertical
transect in Elliott Bay during April 1985 (e), the bold values below and to
the right of the station number are the concentrations from surface samples
(<1 m) collected by small boat.
-90-

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NOAA-EPA
Contaminant Transport Study
l-RERP 85-2
. . ' April 4-5,1985
*rw
Surface
Particulate Al
(|ig/L) >
a
122*20"
290
NOAA-EPA
Contaminant Transport Study
Surface
Particulate
(ue/L.)
c
900
aCSO
800
AI2S889-29.I SaJ (R'sO.91)
700
Put AI=II10-3S.S Sal (Rl=0.75>
ju 500-
3 400
300-
Pift At=S5»-«3.3S*l	"V-
CSO
100-
0 2 4 6 a <0 12 14 16 IB 20 22 24 26 28 30
0 2 4 6 8 10 12 14 16 19 20 22 24 26 28 30
SAUNITY (|/kg)	SALINITY (g/kgj
EB85 Station

* 100
NOAA
Contaminant Transport Study
Particulate
TnfTTrrrvTrrrrnrrrrrn

-------
Figure 11.27. Surface distribution of dissolved Fe in Elliott Bay during
April 1985 and January 1986. Dissolved Fe vs. salinity plots for April 1985
and January 1986. Regression analysis of samples in Elliott Bay are given by
the solid line. Samples in the plumes of the West Duwamish Waterway (WW),
Denny Way CSO (CSO), Harbor Island shipyards (HIS) and the Seattle Waterfront
(SW) are noted and were not used in the regression analysis. A regression
analysis of the samples collected in the West Duwamish Waterway is given by
the dashed line (	). Vertical transect in Elliott Bay during April 1985
(Figure 2e). The bold values below and to the right of the station number are
the values for the surface (<1 m) samples taken by small boat. Figure f is an
expansion of the lower right insert of d.
-92-

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26'
24'
22'
122*20"
39"-

NOAA-EPA


E'.' Contaminant Transport Study


L-RERP 85*2



April 4-5,1985

38'-






• X


4nr-
:




• •

•^4
^8.9


• .

36'-


r4—
¦

Surface • A/

• y


Dissolved Fe # : ^



35'-
(lig/U^f .

|0.6

SALINITY (g/kg)
Dlt Fe=7.0—0.21 Sal (IP=0.77)
nant Transport Study
l-rerp:
January 8-9
Surface
Dissolved
WW
Dls F*s20.S-0.«7 Sal (R*=0.82)
wv»\
WW'v
• sw
Dil Fe=l6.8—0.54 Sal (#=0.98)
CSO
t	!	1	1	r
10 15 20 25 30
SALINITY (g/kg)
EB85 Suuon
<4.4 JqSBDRO,,.,
NOAA-EPA
Conuminant Transport Study
L-RERP 85-2
April 4-5,1965
Dissolved Fe (|ig/L)
n	r
26	28
SALINITY (g/kg)

-------
originating from the East Duwamish Waterway. The salinity plots
(Figs. II.27c-d) reveal that during bath sampling periods the lowest salinity
sample had dissolved Fe concentrations above the mixing line. This indicates
that dissolved Fe from the Duwamish River is being removed from solution in
the low salinity region of the estuary. This phenomenon has been reported by
Boyle et al. (1977), Paulson and Feely (1985) and many others. The change in
the y-intercept of the line used to calculate transport out of the West
Duwamish Waterway vs. the y-intercept of the line used to calculate transport
out of Elliott Bay (Fig. II.27d) indicates that sources from the Seattle
waterfront are causing a slight increase in the amount of dissolved Fe being
transported from Elliott Bay (Table II.6). The mid-depth dissolved Fe
concentration was less than 1 ug/L (Fig. II.27e). The high concentration near
the bottom of station EB85-5 is anomalous. Since dissolved Mn and Pb are
higher at this location, the sediments might be chemically reduced.
Approximately 992 of the Fe in surface and subsurface waters of Elliott
Bay is particulate. Particulate Fe concentrations in surface waters are
highest near the mouth of the Duwamish River and along the Seattle waterfront
(Fig. II.28a,b). The particulate Fe versus salinity plot (Fig. II.28c) for
April, 1985 surface waters is nearly linear, suggesting very little
sedimentation of particulate Fe from the surface plume. This interpretation
is consistent with the results of the suspended matter and salinity
measurements discussed previously. In January, the Denny Way CSO was a
significant source of particulate Fe to the surface waters. A strong south-
to-north gradient of particulate Fe is evident in the outer bay, indicating
that the prevailing cyclonic motion of the surface currents transport
particulate Fe-bearing substances out of the bay along the northern half of
the bay. The particulate Fe versus salinity plot for January, 1986
-94-

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Table II.6. Transport of Dissolved Trace Metals
Transport
April 1985
January
1986

From
From W.
From

Elliott Bay
Duwamish W.
Elliott Bay
Water (m3/sec)
96.0
30.2
30.2
Fe (g/sec)
0.67
0.51(80%)*
0.63

±0.09
±0.04
±0.06
Mn (g/sec)
3.8
1.7(77%)
2.2

±0.1
0.1
±0.1±0.2
Cu (g/sec)
0.077
0.036(32%)
0.11

±0.008
±0.003
±0.01
Zn (g/sec)
0.57
0.41(46%)
0.89

±0.05
±0.04
±0.09
Pb (g/sec)
0.0048



±0.0003


Ni (g/sec)
0.065
0.036(63%)
0.057

±0.005
±0.004
0.006
Cd (g/sec)
—
-
—
1) Error based on error of the y-intercept calculation from regression
analysis.
2) Values in parentheses are the West Duwamish Waterway's contribution to the
total flux out of Elliott Bay.
-95-

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Figure 11.28. Surface distribution of particulate Fe in Elliott Bay during
April 1985 (a) and January 1986 (b). Particulate Fe vs. salinity plots for
April 1985 (c) and January 1986 (d). Results of regression analysis of
samples in Elliott Bay are presented as solid lines. Samples in the plumes of
the West Duwamish Waterway (WW) and the Denny Way CSO (CSO) are noted as open
circles and are not used in the regression analysis. For the January 1986
regression, only samples collected on the day that the CSO discharged were
used in the regression analysis. A regression of the samples collected in the
West Duwamish Waterway is presented as a dashed line (	). In the vertical
transect in Elliott Bay during April 1985 (e), the bold values below and to
the right of the station number are the concentrations from surface samples
(<1 m) collected by small boat.
-96-

-------
NOAA-EPA
Contaminant Transport Study
L-AERP 86-1
January 8-9.1966
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April 4-5,198S
+r3r
Surface
Particulate Fe
(Ug/L)jJ:
c
aoo-
»CSO
ww\p,rt N=WO-3l.7 Sal (R^q.BO
soo
WWo\s\
Pan F«=7«a-li.9 Sal 4 i6 ia 20 22 14 26 2a 30
SAUNITY (t/kti
EB85 Station
SBDRO
247
595
405 ,278
355
100
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April 4-5,1985
ui
O
Particulate Fe (iig/L)
I km
200

-------
(Fig. II.28d) is influenced by the additional input from the Denny Way CSO.
Thus, the calculated transport of particulate Fe from Elliott Bay is about 20%
higher than the transport out of the West Duwamish Waterway (Table II.7).
The vertical transect of particulate Fe (Fig. II.28e) indicates a very
narrow surface plume in the upper 10 meters of the water column. Below this
depth, particulate Fe concentrations decrease steadily to the bottom except
for station 9 where there is some evidence for resuspended sediments in the
bottom 50-70 meters of the water column.
Manganese
Dissolved Mn plumes originating from the West Duwamish Waterway can be
seen during both sampling periods (Fig. II.29a,b) while an additional plume
from the East Duwamish Waterway is evident during the January 1986 period.
The change in the y-intercept of the line used to calculate transport out of
the West Duwamish Waterway vs. the line used to calculate transport out of
Elliott Bay (Fig. II.29c,d) indicate that sources within the East Duwamish
Waterway are causing a slight increase in the supply and transport of
dissolved Mn out of Elliott Bay (Table II.6). The vertical transect indicates
that dissolved Mn at mid-depth ranges between <1 and 2 ug/L (Fig. II.29c).
The vertical transect indicates that dissolved Mn was added to the water
column from sedimentary sources near station EB85-5, possibly as a result of
reducing conditions in the sediments (see discussion on Iron).
Particulate Mn plumes from the Duwamish River are evident during both the
April 1985 and January 1986 sampling periods (Figs. II.30a,b). The Denny Way
CSO was also a significant source of particulate Mn in January. Manganese was
roughly equally partitioned between dissolved and particulate phases in the
water column. The vertical transect (Fig. II.30e) indicates evidence for a
-98-

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Table II.7 Flux of total suspended matter and particulate metals out of
	Elliott Bay (g/sec)	
April 1985		January 1986	
From	From	From
Elliott bay W. Duwamish W. Elliott Bay
Flow (m3/sec)
Total Suspended Matter
A1
Fe
Mn
Cu
Zn
Pb
Ni
96.0
960.0
85.0
± 5.0
99.0
± 5.0
2.0
0.1
0.14
0.01
0.19
i 0.01
0.086
± 0.009
0.053
±0.003
30.0
200.0
17.0 (50%)2
± 1.0
24.0(82%)
± 1.0
0.018
+ 0.001
0.014(24%)
+ 0.003
0.064(46%)
0.003
0.044(29%)
0.004
0.010(29%)
± 0.001
30.0
310.0
34.0
± 1.0
29.0
± 3.0
0.0581
±0.051
0.14
±0.020
0.021
0.003
0.035
0.005
Errors based on one a of the error in the y-intercept of the regression
analysis.
1	Based upon the flux of particulate Fe and a Cu/Fe ratio of 0.0017 ± 0.0015.
2	Values in parentheses are the West Duwamish Waterway's contribution to the
total flux out of Elliott Bay.
-99-

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Figure 11.29. Surface distribution of dissolved Mn in ElLiott Bay durint
April 198S (a) and January 1986 (b). Dissolved Mn vs. salinity plots for
April 198S (c) and January 1986 (d). Results of regression analysis of
samples in Elliott Bay are presented as solid lines. Samples in the plumes of
the West Duwamish Waterway (WW), the East Duwamish Waterway (EW) and the Denny
Way CSO (CSO) are noted as open circles and are not used in the regression
analysis. A regression of the samples collected in the West Duwamish Waterway
is presented as a dashed line (	). In the vertical transect in Elliott Bay
during April 1985 (e), the bold values below and to the right of the station
number are the concentrations from surface samples (<1 m) collected by small
boat. Figure f is an expansion of the lower right insert of d.
-100-

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lb'
Vf
IX
a
112*20'
39"-



E ¦. NQAArErA


g. Contaminant Trailtport Study

L-RERP 8S-2


\z.\- . April 4-S, I98S

3ff-



47*3r-
/ *
10



* I5^i


V / •

It'-i

r20
tl

Surface /'¦ \ l/i



Dissolved Mn A \|/J.


35'-

|: '¦%
&
NOAA-EPA
Contaminant Traniport Study
L-RERP 36-1
Januarys-?, 1986
Surface
Dissolved
(iig/D
Dh Mn=71—2.27 Sal (IP=0.77)
WW N
DIs Mn=3«.7-I.27 Sal (1^=0.99)
WW V V EW
Dli Mn=56—1.75 Sal (R'=0.99) % %
1	1	r
15 20 25
SALINITY (g/kg)
i i r
10 IS 20
SALINITY (g/kg)
EB85 Station
a	SBORO
730.6 fM.1 , 24.6
10 7»
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April 4-5. 1983
Dissolved Mn ((Jg/L)
I
26	28
SALINITY (g/kg)

-------
Figure 11.30. Surface distribution of particulate Mn in Elliott Bay during
April 1985 (a) and January 1986 (b). Particulate Mn vs. salinity plots for
April 1985 (c) and January 1986 (d). The results of the regression analysis
of samples collected in Elliott Bay during April 1986 is presented as solid
line. Samples in the plumes of the West Duwamish Waterway (WW) and the Denny
Way CSO (CSO) are noted as open circles. A line with an adequate regression
coefficient could not be fitted to the Elliott Bay data for January, 1986
samples. A regression of the samples collected in the West Duwamish Waterway
is presented as a dashed line (	). In the vertical transect in Elliott Bay
during April 1985 (e), the bold values below and to the right of the station
number are the concentrations from surface samples (<1 m) collected by small
boat.
-102-

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a	b
24'	14'	22'	122*20'
NOAA-EPA
Contaminant Tram port Study
L-RERP 86-1
January 8-9.I9M
NOAA-EPA
Contaminant Transport Study
L-R6W 8S-2
' April 4-S. 1985
12.1
2.5
•7.5
Surface
Particulate Mir
WUJ:
3.5
d

20-





18-
14-
\ •



1
14-


-

£
§
n-
IQ-


¦
OQO
U
1
a-
6-
4-
2-.
0-
P*rtMr*«20.T-0.6» fel 2 >4 >6 >9 20 22 24 26 28 20
SALINITY (^kt>	SALINITY («/h()
e
EB8S Station
.5BDRO,
3.8
5.2
3.3
17.0
S.I00-
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April 4-5, (985
Particulate Mn (jjg/L.)
TT^fTrr-rrrrrrrrrrrrrrrrr
I km
200

-------
strong vertical gradient of particulate Mn in the water column with a minimum
at about 30-40 meters. The enrichment of particulate Mn in the bottom 30-60
meters of the water column is probably due to the scavenging of manganese
released from sediments (Feely et al., 1983).
Copper
The areal distribution patterns reveal a small plume originating from the
Seattle waterfront in April 1985 (Fig. II.31a) while the vertical transect
(Fig. II.31e) shows a mid-plume surface layer enrichment in dissolved Cu.
Larger and more significant plumes originating from the Harbor Island
shipyards and Denny Way CSO were seen in January 1986 (Fig. II.3lb).
Concentrations of 5900 and 5000 ng/L were found in the Denny Way CSO and the
Harbor Island shipyard plumes, respectively. The large increase in the
y-intercept for the line used to calculate transport out of Elliott Bay in
comparison to the y-intercept for the line used to calculate transport out of
West Duwamish Waterway (Fig. II.31d) indicates that the Denny Way CSO and
Harbor Island shipyards are tripling the transport of dissolved Cu out of
Elliott Bay (Table II.6). The large areal extent of the Harbor Island
shipyard plume suggests that this source is much more significant than the
CSO. The 1985 vertical transect (Fig. II.31e) indicates that mid-depth
dissolved Cu concentration ranged between 300 and 400 ng/L.
The particulate Cu distributions were very similar to the dissolved
distributions, although the mean concentrations in the particulate phase
(100 ng/L) were significantly lower than Cu concentrations in the dissolved
fraction (Figs. II.32a-b). In January, the Harbor Island shipyards and Denny
Way CSO were also major sources for particulate Cu to the surface waters of
Elliott Bay. The calculated transport of particulate Cu from the West
-104-

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Duwamish Waterway in January was 10 times Less than the calculated transport
from Elliott Bay in April (Table II.7). The vertical transect reveals that
the surface plume is the major source of particulate Cu in the bay
(Fig. II.32e). There is a slight enrichment of particulate Cu in the near-
bottom waters of the outer bay, due either to advection of main basin
suspended material or to local resuspension of bottom sediments. Enrichment
of Cu and other trace metals directly north of Harbor Island is probably
related to surface runoff during heavy rainfall.
Zinc
Like Cu, Zn is a relatively soluble metal and can be expected to appear
as a result of surface runoff as well as from point sources with high
particulate loadings. The surface distributions of dissolved Zn were similar
to those of dissolved Cu for both sampling periods. A plume from the Seattle
waterfront is evident in April 1985, as well as high in concentration at the
same station off the head of the West Duwamish Waterway (Fig. II.33a). In
January 1986, larger and more significant plumes can be seen off the Denny Way
CSO and the Harbor Island shipyards (Fig. II.33b) with dissolved
concentrations of 33,000 and 20,500 ng/L, respectively. The change in the
y-intercept of the line used to calculate transport out of Elliott Bay
relative to the y-intercept for the line used to calculate transport out of
the West Duwamish Waterway (Fig. II.33d) suggests that the Harbor Island
shipyards and the Denny Way CSO have increased the transport of dissolved Zn
from Elliott Bay by a factor of 2.5 (Table II.6). The vertical transect
indicates that dissolved Zn concentrations between 500 and 1000 ng/L were
found at mid-depth in Elliott Bay.
-105-

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Figure 11.31. Surface distribution of dissolved Cu in Elliott Bay during
April 1985 (a) and January 1986 (b). Dissolved Cu vs. salinity plots for
April 1985 (c) and January 1986 (d). Results of regression analysis of
samples in Elliott Bay are presented as solid lines. Samples in the plumes of
the West Duwamish Waterway (WW), the Harbor Island shipyards (HIS) and the
Denny Way CSO (CSO) are noted as open circles and are not used in the
regression analysis. A regression of the samples collected in the West
Duwamish Waterway is presented as a dashed line (	). In the vertical
transect in Elliott Bay during April 1985 (e), the bold values below and to
the right of the station number are the concentrations from surface samples
(<1 m) collected by small boat. Figure f is an expansion of the lower right
insert of d.
-106-

-------
26'
24'
22'
I22"20'
39*
38"
47*37'-
36'-

NOAA-EPA

-

. Contaminant Traniport Study


1-REW85-2



..' April 4-5,198S

-
400
1 * \



• I
S00 *



1 •
•fe: .

-
L \ •
•Jjt. ¦
-
Surface

* *1


Dissolved Cu




(ng/O^

f ¦ ''n


NOAA-EPA
Contaminant Tramport Study
L-ft£RP 86-1
January 8-9,1986
Surface
Dissolved Cu
(ng/L)
5000-
5000
4800-

= 3600-j
Q
£
i 2400H
a
5
1200 H
DU Cu=845—14.5 Sal (RJ=0.44)
-»*¦«
WW® 0 WW
~i	1	r
10 15 20 25
SALINITY (g/kg)
SB85 Scation
NOAA-EPA
Contaminant Transport Study
L-R6RP SS-1
April 4-5.1985
Dissolved Cu (ng/L)
~ 4800~
5 3600 H
§ 2400H
8
o
1200
1200
A
cso
•
HIS
Dl» Cu=3540—105 Sal (Rl=0.73)

HI5
0
WW WW N
*		—»^_yywl
DU Cu—1250—28.8 Sal (R]=0.9I j


1 1 1 1
0 5 10 15 20
SALINITY (g/kg)
1 1
25 30
f
1000-
0 400-
200-
ir
26	28
SALINITY (g/kg)

-------
Figure 11.32. Surface distribution of particulate Cu in Elliott Bay during
April 1985 (a) and January 1986 (b). Particulate Cu vs. salinity plots for
April 1985 (c) and January 1986 (d). The results of the regression analysis
of samples collected in Elliott Bay during April 1986 is presented as solid
line. Samples in the plumes of the West Duwamish Waterway (WW), the Denny Way
CSO (CSO), the Harbor Island shipyards (HIS) and the Seattle waterfront are
noted as open circles. A line with an adequate regression coefficient could
not be fitted to the Elliott Bay data for January 1986 samples. A regression
of the samples collected in the West Duwamish Waterway is presented as a
dashed line (	). In the vertical transect in Elliott Bay during April 1985
(e), the bold values below and to the right of the station number are the
concentrations from surface samples (<1 m) collected by small boat.
-108-

-------
24'
39*-
38'-
4rir-
36'-
24'
22'
a
112*20'
35'
E NOAA-EPA
. Contamii
nnt Transport Study
• V.
L-RERP 85-2
^4Q0\V . . . ¦ April 4-5.1985


\ .n

200 1
« ..
1 * 1

W—^ 400 Xv •
"V •
re., ..
\
• , "i<* L
>600 i<5
• \
//\ MW

// 800 |V
Surface jS" ' A*
II* Lrl r*'
Particulate Cuyf . :
(I-

' |.I30
NOAA-EPA
Contaminant Transport Study
January 8-9
Surface
Particulate
(ng/U
IttO-
PwtCu«MII-47.»S«l 
-------
Figure 11.33. Surface distribution of dissolved Zn in Elliott Bay during
April 1985 (a) and January 1986 (b). Dissolved Zn vs. salinity plots for
April 1985 (c) and January 1986 (d). Results of the regression analyses of
samples in Elliott Bay are presented as solid lines. Samples in the plumes of
the West Duwamish Waterway (WW), the Harbor Island shipyards (MIS) and the
Denny Way CSO (CSO) are noted as open circles and are not used in the
regression analysis. A regression of the samples collected in the West
Duwamish Waterway is presented as a dashed line (	). In the vertical
transect in Elliott Bay during April 1985 (e), the bold values below and to
the right of the station number are the concentrations from surface samples
(<1 m) collected by small boat. Figure f is an expansion of the lower right
insert of d.
-110-

-------
16'
39*
3 8-
*nr-
34'-
35'-
24'
22'
a
m"xt
•' '
NOAA-EPA

Contaminant Traniport Study

L-RERP 85-2

April 4*5,1985 ¦
•
I •
1000 /.

1 1 3000Jfe.

12000 . 5^

\ \ 0ooo 'fr
Surface
X i . . £*.-
Dissolved Zn
/.' : 1: '
(ng/L)^
M2280L '

. 11: I r '
Surface
Dissolved Zn
(ng/L)
NOAA-EPA
Contaminant Transport Study
L-RERP 36-1
January 8-9,1986
10,000
33,000
2000 >T^k4000
#)
40001
'4000
32000-
24000-
<5
2 16000-
5
o
v!
a 8000H
Di> Zn =4000—144 Sal =0.82)
vvw# «ww
~i	1	1	1	r~
5 10 15 20 25
SALINITY (g/kg)
EBBS Scation
51988 43SOO ?-.^BPROa00
NOAA4PA
Contaminant Transport Study
L-#ERP 85-2
April 4-5,1985
Dissolved Zn (ng/L)
32000-
i, 24000-
3
5
o
ut
q 8000-
10000-
a
"5b
N
o
ui
5
o
3
Q
8000-
6000-
4000-
2000-
0
cso
0

\DbZn=29500-934Sal (R>=0.7A)

HIS
•
«¦» ^
\
HIS
WW»VV	WW \
ww0*--0^ ^

Ola Zn=l3700-4I4 Sal (R'sO.mT "V
WW

1 1 1 1
] S 10 15 20
1 1*
25 30
SALINITY (g/kg)
f


>V •

.
• V*

*
•
•• ~V.
•
K 1
"I	I	T"
24	26	2fl	30
SALINITY (g/kg)

-------
Although lower in absolute concentration, the trends of particulate Zn
concentrations are very similar to those of dissolved Zn distributions
(Figs. II.34a-b). In April 1985, the highest concentration was observed in
the West Duwamish Waterway. In January 1986, larger plumes of particulate Zn
were observed off the Denny Way CSO and the Harbor Island shipyards where
concentrations as high as 14,500 ng/L were observed. The particulate Zn
versus salinity plots (Figs. II.34c-d) reflect these sources in the solid
line. The mass transport calculations suggest that the CSO and Harbor Island
are doubling the transport of particulate Zn out of Elliott Bay relative to
the transport out of the West Duwamish Waterway (Table II.7). The vertical
transect (Fig. II.34e) indicates very high enrichments in the surface plume
followed by rapid decreases in particulate Zn concentrations in subsurface
waters. There is also evidence for a weak maximum at about 40 m in the inner
bay which is probably the result of Zn scavenging onto newly-formed Mn
oxyhydroxide coatings on the particles (Feely et al., 1983).
Lead
In both sampling periods, the dissolved Pb concentration at the head of
the West Duwamish Waterway was between 40 and 50 ng/L (Figs. II.35a-b). The
Pb-salinity plots for April 1985 (Fig. II.35c) show a constant decrease in the
dissolved Pb concentration with salinity suggesting that there were no other
significant inputs with the possible exception of a small plume near the Denny
Way CSO even though it had not been discharging for over a week, i.e., there
was diffusion of Pb from the most concentrated sources. In January 1986, a
more significant plume having a dissolved Pb concentration of 2570 mg/L can be
seen originating from the Denny Way CSO (Fig. II.35b). Smaller plumes can be
seen off the Seattle waterfront near the King Street CSO, and off the Harbor
-112-

-------
Island shipyards. A regression line having a r2 of greater than 0.5 could not
be drawn through either the Elliott Bay or West Duwamish Waterway data
(Fig. II.35d), indicating a multiplicity of sources, including possibly,
atmospheric deposition. The transect indicates that mid-depth water in
Elliott Bay had dissolved Pb concentrations less than 20 ng/L (Fig. II.35e).
The bottom samples at stations E885-5 and EB85-SBDRQ show enrichments in
dissoLved Pb. The enrichment at EB85-SBDRQ may be due to diffusion of
dissolved Pb out of the highly contaminated sediments of the West Duwamish
Waterway.
Particulate Pb concentrations in Elliott Bay are generally 4-11 times the
dissolved Pb concentrations (Figs. II.36a-b). Major sources for particulate
Pb include the Duwamish River, Harbor Island, the Seattle waterfront and the
Denny Way CSO. In January particulate Pb concentrations near the Denny Way
CSO exceeded 10,000 ng/L* The plume from the outfall was observed to flow
along the northern shore past Pier 91. Beyond Pier 91, particulate Pb
concentrations in the surface waters exceeded or equaled 250 ng/L westward
around Magnolia Bluff. These results provide clear evidence for particulate
Pb transport into the main basin of Puget Sound from Elliott Bay. The mass
transport of particulate Pb out of Elliott Bay is more than three times the
transport out of the West Duwamish Waterway, indicating the significance of
other sources (Table II.7). The transect (Fig. II.36e) indicates that most of
the particulate Pb transport out of the bay is associated with the surface
plume. Beneath the surface, particulate Pb concentrations decrease to values
below 50 ng/L. There is a zone of higher particulate Pb concentrations in
near-bottom waters of the outer bay which is due either to locally resuspended
sediments or advection from the main basin. Both dissolved and particulate Pb
appear to be excellent tracers of surface water movement.
-113-

-------
Figure 11.34. Surface distribution of particulate Zn in Elliott Bay during
April 1985 (a) and January 1986 (b). Particulate Zn vs. salinity plots for
April 1985 (c) and January 1986 (d). Results of the regression analyses of
samples in Elliott Bay are presented as solid lines. Samples in the plumes of
the West Duwamish Waterway (WW), Denny Way CSO (CSO) and the Harbor Island
shipyards (HIS) are noted as open circles and are not used in the regression
analysis. For the January 1986 regression, only samples collected on the day
that the CSO discharged were used in the regression analysis. A regression of
the samples collected in the West Duwamish Waterway is presented as a dashed
line (	). In the vertical transect in Elliott Bay during April 1985 (e),
the bold values below and to the right of the station number are the
concentrations from surface samples (<1 m) collected by small boat.
-114-

-------
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
. April 4-5.198S
47*37"
V
Surface
Particulate Zn
(ng/L)
I22°20'
NOAA-EPA
Contaminant Transport Study
L-RERP 86-1
January 8*9,1986
1,000
500 ft. 14,500
Surface
Particulate Zn
(ng/L)
2500
2250-
2000
> 1750-
r5 (S00-
Pan Zn=2002-6S.I Sal (ft1 =0.91)
2 1250-
p 1000-
B 10 12 14 16 18 20 22 24 26 28 30
Part Zn=4S16-»4* Sal (If =0.81)

Put Zn=ll27-6J Sal (B*=0.«a»
26 28 10
SALINITY (|/k|)
0 2 4 6 S 10 12 14 It IS 20 22 24
SALINITY (g/kS>
EB85 Station
4 -i SBDRO
71257 fl26l , 1456
= 100
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April 4-5.1985
Particulate Zn (ng/L)
tPTH nn/n >n n
200

-------
Figure 11.35. Surface distribution of dissolved Pb in Elliott Bay during
April 1985 (a) and January 1986 (b). Dissolved Pb vs. salinity plots for
April 1985 (c) and January 1986 (d). Samples in the plumes of the West
Duwamish Waterway (WW), the Harbor Island shipyards (HIS), the Seattle
waterfront (SW) and the Denny Way CSO (CSO) are noted as open circles. Lines
with regression coefficients >0.5 could not be fitted to the data for January,
1986 for samples collected from either the West Duwamish Waterway or Elliott
Bay. In the vertical transect in Elliott Bay during April 1985 (e), the bold
values below and to the right of the station number are the concentrations
from surface samples (<1 m) collected by small boat. Figure f is an expansion
of the right insert of d.
-116-

-------
16'
3*
38*
«rjT-
36'
3S'-
14'
a*
a
U2"W

NOAA-EPA
, Contaminant Transport Study
L-RERP 85-1
,.' April 4-5,198S ¦

f f* ii;..
^40"^

•
3°s ^
4;

f•
•J?' •
Surface
Dissolved Pb
(ng/Qvf^
I

NOAA-EPA
Contaminant Transport Study
L-RERP 86-1
January 8-9.1986
Surface
Dissolved Pb
(ng/L)
q 100—
Db Pt>=44HJ.9l Sal
	1	1	1	r
S 10 IS 20 25
SALINITY (g/kg)
EBS5Stnkm
13,
3 m SBDH.O
E.
1.100
«
o
100'


	m ' 1 in	r ' -Sr-** Z-
•
•
•
•
• \
• • If


* ir
jT 5* NOAA-EPA


/ CoAUminant Traniport Study


/ L-0ERP8S-1


/ April 4*5.196S


i i Dissolved Pb (ng/L)
				 1 km
47
100-
5
£
a
§
o
in
i/i
5

cso


1750



sw


0


cso


a


HISo


•


•••


r..
"
WW WW
0 ®
•#

WW WW


o •
• i

1 1 1 1 1 1
O 150-
'ob
c
£
Q IOOH
UJ
a
y»
5 50-H
10 IS 20 25 30
SALINITY (g/kg)
f
'* •* .
*	• • /l
• ~ V
i	r
26	28
SALINITY (g/kg)

-------
Figure 11.36. Surface distribution of particulate Pb in Elliott Bay during
April 1985 (a) and January 1986 (b). Particulate Pb vs. salinity plots for
April 1985 (c) and January 1986 (d). Results of regression analysis of
samples in Elliott Bay are presented as solid lines. Samples in the plumes of
the West Duwamish Waterway (WW), the East Duwamish Waterway (EW) and the Denny
Way CSO (CSO) are noted as open circj.es and are not used in the regression
analysis. For the January 1986 regression, only samples collected on the day
that the CSO discharged were used in the regression analysis. A regression of
the samples collected in the West Duwamish Waterway is presented as a dashed
line (	). In the vertical transect in Elliott Bay during April 1985 (e),
the bold values below and to the right of the station number are the
concentrations from surface samples (<1 m) collected by small boat.
-118-

-------
16'
jr-
18*-
14'
12'
a
iuuo'
47*37'-
36-
35'-
NOAA-EPA
Contaminant Transport Study
"¦"Jirtnfe-1 ' ' L-RERP 85-1
April 4-5, 1985
>>300>%i^jjjt.

\<®-4IS

200 ^
\ 1*°$
•V-; . .
\ I |* \ \

Vn 11 400
Surface /' \* 1 I *. V;
Particulate Pby \1
("g/U^ ' • • 63.3
P?r:'.
NOAA-EPA
Contaminant Transport Study
L-RERP 86-
lanuary B-9,1906
.750
sodito. 10.200
-100
Surface
Particulate Pb
(ng/L)
c
1500
1250
\ Pan	Sal (AJ=fl.7*)
> 1000'
7S0'
ww©
-vlAew,
P«itftsMU-)S.?Sal{R,«0.n) V "v \i/
WW	\T
cso
PbBttt-26.7 Sal (R'ssO-M)
soo-

250'
0 1 ~ i 9 10 II H i* 19 20 2! 24 24 38 30
0 2 4 (, G 10 12 H l« 10 20 22 24 34 2B 30
SALINITY	SALINITY {(/kg)
EB85 Station
f 472 ?47SSB?R0633
5 100
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April 4-5,1985
Particulate Pb (ng/L)
tipTTrn trrrrnftrt rrt

-------
Nickel
The surface distribution of dissolved Ni for April 1985 reveals only a
decreasing gradient from east to west the plume (Fig. II.37a). The Ni vs.
salinity plot (Fig. II.37c) shows a slight increase in dissolved Ni with
distance away from the head of the West Duwamish waterway indicating the
presence of another source of dissolved Ni. In January 1986, plumes can be
seen which originate from the Denny Way CSO and from a combination of sources;
from the East and West Duwamish Waterways and Harbor Island shipyards
(Fig. II.37b). Sources other than those from the West Duwamish Waterway
increase the transport of dissolved Ni out of Elliott Bay by 60%
(Table II.6). Dissolved Ni concentrations less than 400 ng/L were found at
mid-depth in Elliott Bay.
Particulate Ni concentrations were generally about 20-60% of the
dissolved concentrations (Fig. II.38a-b)._ High values were observed at the
mouth of the Duwamish River in April and January and seaward of the Denny Way
CSO in January. The highest concentrations (>1000 ng/L) were observed in the
immediate vicinity of the outfall in January. The concentration gradients of
particulate Ni indicate flow to the northwest along the northern shore. The
particulate Ni transport out of Elliott Bay is twice the transport from the
West Duwamish Waterway (Table II.7). In subsurface waters particulate Ni
concentrations reach a minimum (<20 ng/L) between 20 m and 60 m and increase
slightly near the bottom (Fig. II.38e).
-120-

-------
Chromium
Particulate Cr concentrations in ElLiott Bay ranged from 20 to 1444 ng/L
(Fig. 11.39). High concentrations were observed at the mouth of the Duwamish
River in April and January and seaward of the Denny Way CSO in January. The
highest concentrations <> 1440 ng/L) were observed in the immediate vicinity
of the CSO outfall in January. The concentration gradients of particulate Cr
suggest that most of the particulate Cr is transported to the northwest along
the northern shore. In subsurface waters particulate Cr concentrations reach
a minimum between 20 m and 60 m and increase slightly near the bottom
(Fig. II.36a).
Cadmium
Unlike the other metals shown thus far, dissolved Cd concentrations in
the West Duwamish Waterway were lower than those in Elliott Bay
(Figs. II.40a-b). The ocean constitutes a much larger mass source of Cd than
do human inputs. Although the Cd vs. salinity plot for April 1985 shows a
increase in dissolved Cd with salinity, a regression line having a r2 greater
than 0.5 could not be drawn (Fig. II.40c). Plumes originating from the Denny
Way CSO and the Harbor Island shipyards can be seen in the surface
distribution for January 1986 (Fig. II.40b). Dissolved Cd concentrations
greater than 75 ng/L were found at mid-depth in Elliott Bay (Since 90% or more
of Cd is in the dissolved form we chose to measure only that form).
Temporal Changes in the Concentrations of Cu, Zn and Pb in the Upper Layer of
Elliott Bay.
Samples collected from Elliott Bay during 1980 and 1981 showed high
concentrations of dissolved Cu, Zn and Pb relative to other areas in Puget
Sound (Paulson and Feely, 1985). Since 1981, local, state and federal agencies
-121-

-------
Figure 11.37. Surface distribution of dissolved Mi in Elliott Bay during
April 1985 (a) and January 1986 (b). Dissolved Ni vs. salinity plots for
April 1985 (c) and January 1986 (d). Results of regression analysis of
samples in Elliott Bay are presented as solid lines. Samples in the plumes of
the West Duwamish Waterway (WW), the Harbor Island shipyards (HIS) and the
Denny Way CSO (CSO) are noted as open circles and are not used in the
regression analysis. A regression of the samples collected in the West
Duwamish Waterway is presented as a dashed line (	). In the vertical
transect in Elliott Bay during April 1985 (e), the bold values below and to
the right of the station number are the concentrations from surface samples
(<1 m) collected by small boat. Figure f is an expansion of the lower right
insert of d.
-122-

-------
a
26'	24'	22'	122*20'
£ . NOAA-EPA

ftContaminant Transport Study
L-RERP 85-2

N£y'.'. April 4-5,198S

/ •


•
•
Ml
O
?

400



•


•



G£l
Surface -V
• p

Dissolved Ni /¦
i

(ng/Lj^f
if'}

c
1000
800-
-J
Dil Ni=633-9.5 Sat (R>=0.74)
WW
ui
a
WW
400
O
3
Q
200-
0
10
15
20
30
5
25
SALINITY (g/kg)
EB85 Station
'320
S30
f 100
200
5*0 WB°RO490
I km
NOAA-EPA
Contaminant Transport Study
L.ft£RP 85-2
April 4-5, 1965
Dissolved NI (ng/L)
500-
b
NOAA-EPA
Contaminant Transport Study
L-RERP 86-1
January 8-9.1986
400
• •
600
Surface
Dissolved Ni
(ng/L) .*<
400
710
Oh Ni=l950—52 Sal (Rl=0.59)
1000-
cso
oHIS
N WW
800
Db Ni=ll9J—29 Sal (Rl=0.93) s
WW
200-
0
5
10
15
20
SALINITY (g/kg)
f
1000-
• HIS
800-
o «°-
(/>
t/j
5 200-
24
26
28
30
SALINITY (g/kg)

-------
Figure 11.38. Surface distribution of particulate Ni in Elliott Bay during
April 1985 (a) and January 1986 (b). Particulate Ni vs. salinity plots for
April 1985 (c) and January 1986 (d). Results of the regression analyses of
samples in Elliott Bay are presented as solid lines. Samples in the plumes of
the West Duwamish Waterway (WW), the Harbor Island shipyards (HIS) and the
Denny Way CSO (CSO) are noted as open circles and are not used in the
regression analysis. For the January 1986 regression, only samples collected
on the day that the CSO discharged were used in the regression analysis. A
regression of the samples collected in the West Duwamish Waterway is presented
as a dashed line (	). In the vertical transect in Elliott Bay during April
1985 (e), the bold values below and to the right of the station number are the
concentrations from surface samples (<1 m) collected by small boat.
-124-

-------
26'
14'
22'
a
39*-

NOAA-EPA


k. P.'
. C«ntaminint Transport Study


L-RERP 85-1



. ¦ April 4-5,198S

sr-
vx



\
100


irrr-
\«



•T\,
V *



•

34'-

• \ A200
9jS$ '. ¦

Surface



Particulate Ni /


35'-
(ng/U^


NOAA-EPA
Contaminant Traniport Study
1-R0W86-I
January 8-9,1986
Surface
Particulate Ni
(ng/L)
Pvt NI=SI3-I».J Sal (R'=0.»1)
2 300'
i
U 200
PartNI=697-n.3 Sal (lPsO.71)
\ u|<
PtnNI=132-9.44 Sal 
I I I I I	1 I
18 20 22 24 26 28 30
EB85 Station
l386
?2B8 ?334SB9R°459
S 00
NOAA-EPA
Contaminant Transport Stud/
L-RERP 85-2
April 4-5,1985
Particulate Ni (ng/L)
nfll'iiiiiiinihiiiirrn
200

-------
Figure 11.39. Surface distribution of particulate Cr in Elliott Bay during
April 1985 (a) and January 1986 (b). Particulate Cr vs. salinity plots for
April 1985 (c) and January 1986 (d). Results of the regression analyses of
samples in Elliott Bay are presented as solid lines. Samples in the plumes of
the West Duwamish Waterway (WW), the Harbor Island shipyards (HIS) and the
Denny Way CSO (CSO) are noted as open circles and are not used in the
regression analysis. For the January 1986 regression, only samples collected
on the day that the CSO discharged were used in the regression analysis. A
regression of the samples collected in the West Duwamish Waterway is presented
as a dashed line (	). In the vertical transect in Elliott Bay during April
1985 (e), the bold values below and to the right of the station number are the
concentrations from surface samples (<1 m) collected by small boat.
-126-

-------
NOAA-EPA
Contaminant Transport Study
L-REW 84-1
January 8-9,1986
*7*37'
122 20
NOAA-EPA
Contaminant Transport Study
L-RERPaS-l
April 4-S, 1985
too ,s
c
1800
cso
Part Cr3l7l4-S8 Sal {#**9.94}
Pan 0=1173-37.1 Sal (tfsO.JI)
600
400'
CSO
200'
Part Cr«7»-23.l Sal (R>=0.99)
0 2 4 6 8 10 12 14 r6 18 2D 22 24 26 28 30
SAUNirr (|/k|)
SALINITY (f/kg)
EB8S Station
13
e
5670 1 967 ?I04|SBDROI380
S 100
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April 4-5,1985
Particulate Cr (ng/L)
iffrmvmrrrrrrrTwfrrf

-------
Figure 11.40. Surface distribution of dissolved Cd in Elliott Bay during
April 1985 (a) and January 1986 (b). Dissolved Cd vs. salinity plots for
April 1985 (c) and January 1986 (d). Samples in the plumes of the Denny Way
CSO (CSO) and the Harbor Island shipyards (HIS) are noted as open circles.
Lines with adequate regression coefficients could not be fitted to any data
set. In the vertical transect in ELliott Bay during April 1985 (e), the bold
values below and to the right of the station number are the concentrations
from surface samples (<1 m) collected by small boat. Figure f is an expansion
of the lower right insert of d.
-128-

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26'
3»-
38
47*37'-
36'
35'
24'
22'
a
I22-20"

NOAA-EPA
Contaminant Transport Study
L-RERP 8S-2
. April 4-S, I98S






•





80
•
%2£. ¦
¦
Surface
Dissolved Cd
(ng/LAj/



-
• •
NOAA-EPA
Contaminant Transport Study
L-RERP 34-1
January 8-9,1986
Surface
Dissolved Cd
(ng/L)
—J 100-
EB8S Station
I3«
"I	1	T
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SALINITY (g/kg)
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11V
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NOAA-EPA
Contaminant Transport Study
L'fcERP BS*1
April 4-S. 1985



Olssohred Cd (ng/L)


1 km
250
200
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s 150'
s
i100
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SALINITY (g/kg)

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have initiated pollution abatement programs in the Duwamish Waterway and
Harbor Island area. In order to evaluate the effects that these programs
might have had on the water quality of Elliott Bay, a comparison was made
between the data collected in 1985 and 1986 and data collected in 1980 and
1981 (Figs. II.41-11.42). Concentrations of dissolved Cu in 1985 and 1986
were slightly lower than samples collected in 1980 and much lower than those
collected in 1981. In contrast, little change in dissolved Zn can be seen
between samples collected in 1981 and 1985. The most dramatic decrease can be
seen in the dissolved Pb data. The concentrations of samples collected off
the head of the West Duwamish Waterway in 1985 and 1986 are lower by an order
of magnitude or more relative to samples collected in 1981.
Particulate Cu and Zn concentrations showed no decrease during the
interval. Particulate Pb concentrations have increased (Fig. 11.42); probably
due to the higher flow rates during 1985 and 1986 sampling period since the
transport of particulate Pb is similar (Table II.8).
Dissolved trace metals being transported from Elliott Bay originate from
quantifiable sources upstream of the Duwamish Waterway (Green River water and
Renton Sewage Treatment Plant effluent) and non-quantifiable sources in the
Waterway or on Elliott Bay. Since the concentration of dissolved trace metals
is not a function of flow rate (Curl et al., 1982), the transport of dissolved
trace metals from the Green River will increase proportionately with flow
rate. If the amount of dissolved trace metals discharged into the Waterway or
from the Elliott Bay shoreline is constant and not a function of flow rate,
increased flow from the Green River will tend to dilute these discharges.
Therefore, it is possible that the lower concentrations seen in 1985 and 1986
compared to the concentrations found in 1980 and 1981 are a result of higher
flow rates which occurred during the recent sampling. In order to distinguish
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Table II.8. Apparent Dissolved Inputs Downstream of the Turning Basin
	April, 1980	August, 1981	April, 1985	January, 1986	
Flow (m3/sec)	17 9.2	90	30
Dissolved Cu	0.21 0.36	0.011	0.08
(g/sec)	(0.23,0.01,0.01) (0.38,0.01,0.01)	(0.077,0.056,0.01)	(0.11,0.02,0.01)
Particulate Cu	?	?	?
(g/sec)	(0.034,?,0.001)	(0.14,?,0.001)	(0.058,?,0.001)
Dissolved Zn	1.0	0.43	0.82
(g/sec)	(1.1,0.01,0.04)	(0.57,0.10,0.04)	(0.89,0.03,0.04)
Particulate Zn	?	?	?
(g/sec)	(0.12,?,0.004)	(0.19,?,0.004)	(0.14,?,0.004)
Dissolved Pb	0.42	0.0		
(g/sec)	(0.42,0.001,0.01)	(0.0048,0.002,0.01		
Particulate Pb	111
(g/sec)	(0.055,?,0.01) (0.086,? ,0.01)	(0.151,?,0.01)
The calculation used to calculate the apparent flux downstream of the turning basin is shown
in the parenthesis (a,b,c) where a is the apparent flux of dissolved metals from Elliott Bay;
b is the flux of dissolved trace metals in Green River water (average concentration 620, 1100
and 20 ng/2, for dissolved Cu, Zn and Pb, respectively) and c is the dissolved trace metal
flux from the Renton Sewage Treatment Plant.
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Figure II.41. Regressions of salinity and dissolved trace metals in the upper
layer of Elliott Bay. Dissolved Cu (a and d), Zn (b and e) and Pb (c and f)
during 1980 (A), 1981 (B), 1985 (& ) and 1986 (O). Figs, d, e and f are
enlargements of the high salinity regions of a, b and c, respectively.
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2000
1600-
U
b 1000H
5
3
u
fe 500-
<
°	a ° o°
o • . &o
"I—1—I—I—I—I—I—I—I—I—I—I—I


2000-


c

N
1500-
h

3

o
u
1000-
g

&
<

a.
500-

1750-
1500-
c

J3
a.
1250-
UJ
§
1000-
—j
3
750-
U
<
500-
a.


250-
'4
0 2 4 6 8 10 12 14 16 18 20 22 24 26 28 30
SALINITY (g/kg)

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Figure 11.42. Figure 11.58. Regressions of salinity and particulate trace
metals in the upper layer of Elliott Bay. Particulate Cu (a), Zn (b) and Pb
(c) during 1981 (¦), 1985(A) and 1986 (O).
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2000-
1500-
q 1000-
iii
3
§
o
500-
0H—i—i—i—i—i—i—i—i—i—i—i——r—i—r
8000
7000-
6000-
5000-
4000-
3000—
2000-
1000-
0-1—i—i—i—i—i—r
° V
1500
£
2
2
o
1200-
2000
1500-
7000-
6000-
5000-
4000-
3000-
1000 -
0 2 4 6 8 10 12 14 16 18 20 22 24 26 28 30
SALINITY (g/kg)
300-
200-
100-
24
o a o
° 0	°o °0A
26	28
SAUNtrr (g/kg)
30

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between Che effects of flow rate and temporal changes in the anthropogenic
input on the transport of dissolved metals from Elliott Bay, we attempted to
subtract the inputs of Green River water and Renton Sewage Treatment Plant
effluent from the apparent transport of dissolved trace metals from Elliott
Bay (Table II.8). These calculated values are attributable to discharges from
Duwamish Waterway and Elliott Bay sources. From this analysis, it can be seen
that the decreased dissolved Pb concentrations found in 1985 are not due to
effects of river flow but are due to decreased inputs of dissolved Pb from
sources downstream of the turning basin. This analysis indicates that the
discharge of dissolved Cu downstream of the turning basin has also decreased
by a factor of about 5. In contrast, little change in the discharge of
dissolved Zn was found.
Could the existing pollution abatement programs have caused such a large
decrease in the transport of dissolved Pb? METRO reports (Harper-Owes, 1983;
Gamponia et al., 1986) have determined that storm water systems draining the
site of the Harbor Island secondary lead smelter have been responsible for
high concentrations of Pb in the sediments and water column of the West
Duwamish Waterway. The Duwamish Industrial Non-Point Source Investigation has
found total Pb concentrations between 1,400,000 and 2,300,000 ng/L in storm
water from this drain (J. Shahan, METRO, pers. com.). Twenty-two (22%) of the
total Pb from this storm drain was in the dissolved form (Harper-Owes,
1983). Since dissolved chloride ions in seawater can solubilize lead from
sediments, particulate lead in these storm drains could also contribute to the
dissolved Pb load once they were introduced into the saline waters of the West
Duwamish Waterway. Between the earlier sampling period in Elliott Bay (1981)
and the present investigation (1985-1986), the secondary lead smelter ceased
smelting operations (1984), the storm drains were cleansed of their residual
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sediments (1984) and parking lots in the vicinity of the secondary lead
smelter were paved in 1983 to control fugitive dust. Because of the extremely
large source of dissolved lead associated with post smelter operations, these
removal and control measures could explain the dramatic decrease in the
concentration of dissolved Pb in Elliott Bay.
The concentrations of particulate metals in 1985 and 1986 were also lower
than those found in 1981 (Fig. 11.42). However, these decreases seem to be
more related to flow rate effects since the transports of particulate Cu, Zn
and Pb from Elliott Bay were higher during the high flow periods of 1985 and
1986 relative to the lower flow periods of 1981 (Table II.8). Since total
suspended matter concentration varies with river flow rate, an analysis to
separate flow rate effects from temporal changes in the discharge of
particulate tract metals can not be made. The concentrations of Pb on the
suspended matter also provide evidence for flow rate effects. Although the
particulates in the storm sewer draining the secondary smelter contained
20-402 Pb by weight, they are diluted by less concentrated riverine
particulates both in the water column and in the sediments of the Duwamish
Waterway. Pb concentrations in the sediments near the discharge point of this
sewer had concentrations as high as 13,000 ppm, indicating that some of the
particulate Pb discharged by the storm drain settled nearby. The degree of
dilution that the particulates from the storm drain will attain in the water
column will depend on the overall suspended load. The increase in suspended
load (from 3 mg/1 in 1981 to 4 mg/1 in 1986) is partly responsible for the
decrease in the particulate Pb concentrations on suspended matter (490 ppm in
1981 vs. 220 ppm in 1986). Since the Duwamish Waterway contributed only about
30% of the particulate Pb flux into Elliott Bay (Table II.8) in January, 1986;
variations in the particulate Pb flux from other sources along ElLiott Bay
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probably obscure any decrease as a result of pollution abatement programs.
These other sources include atmospheric deposition from automobile exhaust,
which should decrease dramatically over the next few years.
II.1.5.2. Toxic Organics
Poly Aromatic Hydrocarbons (PAH)
The concentration of PAH entering Elliott Bay from the surface waters of
the Duwamish River in April of 1985 was quite low (1 ug/g) (Fig. 11.43). This
concentration is similar to that found in the relatively pristine Admiralty
Inlet in 1980 (Bates et aI., 1987). Suspended particulates from the near
bottom waters, however, showed levels of PAH four times higher than the
highest concentrations measured on suspended or settling particulates from the
main basin (Bates et al., 1987). The surface concentrations in Elliott Bay
were high both along the waterfront (5.2 ug/g at station 2) and off Pier 90
(5.2 ug/g at station 3), suggesting sources in these areas. The PAH
concentration was lower at station 4 located at the outer edge of Elliott
Bay. The concentration decreased slightly with depth at station 4 and was
similar to concentrations measured in central Puget Sound off Meadow Point
(Bates et al., 1984). The concentration of PAH on settling particulates at
station 3 also decreased with depth in the water column from 4.4 ug/g at 6 m
to 3.7 ug/g at 95 m. These concentrations are similar to those obtained in
the bottom sediments in this region (Romberg et al., 1984).
PAH concentrations for all Elliott Bay surface samples taken in January
1986 were much higher than those of April 1985, reflecting the higher urban
runoff. Extremely high concentrations were found off the Denny Way CSO site
(35 ug/g at station 5) and at the mouth of the Duwamish River (18 ug/g at
station 1). PAH levels along the waterfront were (Sta. 2) somewhat lower, but
twice as high as those found in April 1985 (11 vs. 5.2 ug/g)«
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PAH distributions in the sediments of ELLiott Bay decrease in a seaward
direction from 3.0 ug/g off the mouth of the river to 1.5 ug/g at the outer
edge of Elliott Bay (Bates et al., 1987, Fig. 11.44.). These sediment data
and the high level of PAH in the suspended particulates from the bottom waters
at station 1 (14 ug/g) indicate that Che Duwamish River is an important source
of PAH to Elliott Bay. Hamilton et al. (1983) have shown that during Low flow
conditions particulate hydrocarbons in the surface waters of the lower
Duwamish River are deposited in the fine-grained sediments of the river bed.
These sediments are resuspended in the salt wedge and transported upstream
with the tidal flow. Although the majority of the particles are sedimented in
the river bed, necessitating periodic dredging, it is likely that some
fraction of these PAH-Laden particles are discharged directly to Elliott
Bay. This would produce the seaward decrease in PAH distribution observed in
Elliott Bay (Fig. 11.44) (Bates et al., 1987; Romberg et al., 1984).
The elevated concentrations of PAH in surface waters at stations 2 and 3
relative to station 1 (5 vs. 1 ug/g) in April 1985 indicate that the West
Waterway of the Duwamish River is not the major source of PAH to surface
waters in Elliott Bay during this period. The East Waterway is a source of
particulate matter to Elliott Bay (see vertical distribution of SPM
(Fig. 11.16.) transect E—E*) and is Likely contributing some PAH in the same
way as is the West Waterway. In the absence of rainfall, PAH sources such as
industrial discharges, creosote pilings (Lake et al., 1979), and aeoLian
combustion products might contribute to elevated concentrations in Elliott
Bay. For two days prior to our sampLing in April there had been measurabLe
rainfalL in the area and trace rainfall on the two sampling days (NOAA NWS,
1985, 1986). Storm drains along the waterfront collect and discharge urban
runoff directly into Elliott Bay for all rainfall events. The vertical
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Figure 11.43. PAH station locations and concentrations in Elliott Bay.
Suspended particulates were collected by centrifuge (open bars) in April 1985
and January 1986 at the surface and, in some cases, at 20 m depth. Settling
particulates were collected by sediment trap (hatched bars) during March to
June 1985.
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PAH CONCENTRATIONS IN ELLIOTT BAY
122° 22'
38'-
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2, 86-1
^ April 4-5, 1985
January 8-9, 1986
PIER 91
DENNY WAY CSO
DUWAMISH HEAD
WEST DUWAMISH WATERWAY:
: EAST DUWAMISH WATERWAY-
A A A J
Station
CD CENTRIFUGED SAMPLES
A AprM 1985
J January 1986
S Surface (SI, S2; duplicate*)
¦3 SEDIMENT TRAP SAMPLES
wMf/Vi'k
mm
Station 2
Station 3
A A
Station 4
Station 5

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Figure 11.44. PAH in sediments of Elliott Bay (After Romberg et al., 1984;
Bates et al., 1987).
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Contour map of High Molecular Weight or Combustion PAH
concentrations in surface sediment grab samples collected from Elliott Bay
(Dots represent data points.)
L-ft
Elliott Bay
Alki Point
HIGH PAHs
(ng/g dry weight)
RANGE SCALE
1	= <3000
2	= 3000 - 6000
3	= 6000 - 12,000
4	= 12,000 - 24,000
5	= >24,000
O Disposal
Area

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distribution of suspended particulate matter (Fig. 11.17) indicates particle
sources for several locations where storm drains are known to exist
(Evans-Hamilton, 1986), for example Pier 89. No discharge data are available
for these storm drains, but increased particle concentrations suggest the
possibility of urban discharges which would elevate the PAH levels in these
areas. High concentrations of PAH in the sediments along the waterfront
(Fig. 11.44) support the claim that this area is a contributor of PAH to
Elliott Bay.
The PAH concentrations on suspended, settling, and sedimented
particulates at station 3 support a downward flux of PAH from the surface
waters to the bottom sediments. However, the particulate flux from the
surface waters to the bottom sediments is a small part of the total
particulate transport out of Elliott Bay (Baker et a1., 1983). The decreasing
concentration of PAH from station 3 to 4 could result from dilution, although
the paucity of data make it impossible to correlate this dilution with the
increasing salinity.
The PAH concentrations on suspended particulates in the surface waters of
Elliott Bay in January 1986 were much higher than those measured in April
1985. The concentration measured in the surface waters at the mouth of the
Duwamish River in January of 1986 was very high (18 ug/g). This high
concentration is most likely due to effluent from the combined sewer overflows
and storm drains discharging into the West Waterway. The Harbor CSO is known
to have discharged 160,000 gallons of effluent into the West Waterway during
our January 1986 sampling period (L. Wharton, METRO, personal
communication). The volume of discharge for METRO CSOs is monitored, but no
PAH concentration information is available. PAH concentrations in CSO
discharges would be largely dependent on the fraction of urban runoff, since
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this is supposed to be the major source of PAH to CSO discharges. If we use a
low PAH loading factor for urban runoff of 0.4 mg/L (Tetra Tech, 1986), a PAH
concentration of 0.1 ng/L can be estimated in the West Waterway surface waters
for this CSO event. All urban runoff collected by the 12 storm drains from
the mouth of the West Waterway to the southern end of Harbor Island discharges
directly into the West Waterway (J. Talbot, City of Seattle, personal
communication). There is no monitoring of these discharges, so volumetric and
PAH concentration data for our sampling period are not available. Pollutant
loading of urban effluents is difficult to assess. It depends on local land
use, traffic volume, road surface type, rainfall duration and storm
intensity, and can vary by as much as two orders of magnitude (Zawlocki,
1981).	We can, however, make some estimates based on drainage area and an
average PAH loading factor. The 7 major storm drains in this area collect
rainfall from 1569 acres (Tetra Tech, 1986). PAH concentrations of 9.4 ng/L
and 52 ng/L at the mouth of the West Waterway were estimated for this storm
event using low and high PAH loading factors, respectively (Appendix XIV).
Although these estimated concentrations neglect PAH contributions from other
local or upstream sources, our concentration of 47 ng PAH/L measured at the
mouth of the West Waterway (Station 1) agrees quite well.
Extremely high concentrations were measured near the Denny Way CSO
(34 ug/g). High concentrations of PAH in the surface sediments in the region
of the CSO (Romberg et 
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correlate well with flow or total suspended solids (Eganhouse and Kaplan,
1981). Annual CSO discharges to Elliott Bay can vary by as much as an order
of magnitude, making estimates of total annual PAH discharge to Elliott Bay
difficult.
Chlorinated Hydrocarbons
The concentrations of polychlorinated biphenyls measured in this study
were in all cases near or below the limit of quantification. DDT and its
breakdown products DDD and DDE were in all cases below our detection limits
(Appendices XI-XIII). This suggests that the present input of chlorinated
hydrocarbons to these embayments is quite low. This is not surprising since
the use of PCB has been largely curtailed since 1976 (Cairns and Siegmund,
1981) and DDT use was prohibited in 1972. Concentrations of certain PCB
isomers in surface waters were approximately ten times greater in January 1986
than in April 1985; at both times however concentrations were still extremely
low (<90 ng/g). PCB was been measured in the Duwamish River in high
concentrations in 1974 following the spill from an electrical transformer
(Hafferty et al., 1977). Sediment from five storm drains discharging to the
Duwamish River were also found to have high concentrations (100,000 ng/g) of
PCB (Tetra Tech, 1986). Combined sewer overflow and storm drain collection
basins apparently can trap some of their particulate load for considerable
periods of time. Small amounts of particulate PCB can then be discharged
years after their deposition when high flow conditions scour the pipes. The
dramatic effect of cleaning these pipes is suggested elsewhere in this report
(p. 123) by the reduction in Elliott Bay lead concentrations following cleanup
of discharge pipes near a lead smelter on Harbor Island. Chlorinated
hydrocarbons are still present in the bottom sediments of Elliott Bay. Their
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distribution in the sediments suggests sources from the Duwamish River, the
dredge spoil site at Four Mile Rock, and the CSO at Denny May (Romberg et ai.,
1984).
II.1.5.3. Summary
The West Duwamish Waterway, Harbor Island and Denny Way CSO sites were
always enriched over Elliott Bay mid-depth concentrations, with the exception
of Cd (Table II.9.). Sources from the West Duwamish Waterway dominated the
distributions of dissolved and particulate trace metals during the high river
flow period of April, 1985. The plume from the West Duwamish Waterway was
confined to a very thin surface layer (<2 m). This feature enhanced the
transport of particulate matter out of Elliott Bay. Plots of salinity versus
dissolved and particulate trace metals suggest that toxic trace metals are
essentially conservative within Elliott Bay during this period. This would
suggest that the majority of metals which emanate from the Duwamish Waterway
enter the main basin of Puget Sound without much loss. Comparisons between
horizontal fluxes and vertical flux indicate that less than 3% of the
particulate matter in the surface lens was lost from the water column due to
settling (Table 11.10).
The surface distribution of particulate PAH in April, 1985 was distinctly
different from the distribution of trace metals. The highest concentration of
PAH was found along the Seattle Waterfront; the Duwamish Waterway was not a
major source of PAH at this time.
The distributions of particulate and dissolved trace metals were strongly
affected by combined sewer overflow events during January, 1986. In addition,
plumes of particulate and dissolved Cu and Zn were discovered north of the
shipyards on Harbor Island. Calculations indicate that transport of Cu, Zn
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Table II.9. Enrichments of Trace Metals in surface plumes in Elliott: Bay.
Enrichments1 (Relative to mid-depth)
April 1985 	January 1986
Element
mid-depth
Cone.
W. Duwamish
Waterway
W. Duwamish
Waterway
Harbour Is.
Shipyards
Denny Way
CSO
Fe
0.4 yg/L
27.5
44.5
3.2
14.3
Mn
1.15 ug/L
20.5
33.2
7.8
12.3
Cu
360 mg/L
0.38
1.6
12.9
16.4
Zn
640 mg/L
2.56
13.4
31.0
50.5
Pb
15 mg/L
2.1
1.6
7.1
170
Ni
380 mg/L
0.28
1.4
1.8
1.7
Cd
80 mg/L
-0.49
-0.2
0.9
2.1
Enrichments are multipliers, indicating how much more concentrated a surface
sample is compared to the mid-depth sample.
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Table 11.10: Horizontal and Vertical Flux of suspended matter and
particulate trace metals in Elliott Bay during April 1985.
Parameter
Horizontal
Flux
(gm/sec)
Vertical
Flux
(gm/sec)

VerticaL Flux
Horizontal Flux
(%)
Suspended Matter 960.0
34.0

3.5
Mn
2.0
0.016

0.3
Cu
0.14
0.0011

0.8
Pb
0.086
0.0021

2.4
Table 11.11
. Order-of-magnitude calculation of the flux of trace metals from
the Denny Way CSO during the January 8th storm
Element
Dissolved


Particulate

FCSO FCS0
FSC0
FCS0
FCS0 FCSO

feb
gm/sec %
(FEB~FDW>
%
gm/sec
feb (feb_fW
% %
A1


1.5
4 9
Fe
0.01 2
9
1.5
10 30
Mn
0.03 1
6
0.02
—
Cu
0.01 9
14
0.01
17 23
Zn
0.06 7
13
0.03
21 39
Pb
0.005
—
0.02
13 20
Ni
0.002 4
10
0.002
6 8
where ^SO' Fg.3 and F^y are the fluxes from the CSO, out of Elliott Bay and
out of the Duwamish Waterway. Numerical, values are given for the CSO
only. ^gB~FDW rePresents the flux of metals into Elliot Bay from
unquantiried shoreline sources. ^cS0^FEB"~FDW^ represents the portion
of this flux which the CSO would have contributed if the average
concentration of the CSO effluent was equal to the CSO effluent
concentration when station SI was sampled.
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and Pb out of Elliott Bay was enhanced 2 to 3 times compared to that
transported out of the West Duwamish Waterway.
The Denny CSO and West Duwamish Waterway were the major sources of PAH in
the January, 1986 sampling period. The levels are extremely high and are
probably due largely to particulate PAH washed off the city streets by rain.
PCB concentrations were also higher in January, suggesting scouring of storm
drain and CSO pipes containing PCB deposited in previous years.
These observations indicate that there are significant sources of
contaminants from many sources along Elliott Bay's shores. The quantification
of these sources requires both concentration and flow data. Although precise
estimates of contaminant fluxes from the Denny Way CSO can not be made, the
availability of CSO flow data allows one to perform an order-of-magnitude
estimate. Assuming that samples SI and J1 were one-third CSO effluent and
two-thirds seawater based on their salinity, an assumed CSO effluent
concentration can be calculated. By multiplying this assumed effluent
concentration by the average CSO flow for the duration of the overflow event
(0.6 m3/sec), an order-of-magnitude estimate of the CSO contaminant flux was
made and is shown in Table 11.11.
These order-of-magnitude estimates can be compared to the fluxes of
metals out of the Duwamish Waterway (Egy) and Elliott Bay (Fgg)» Assuming
conservative behavior in Elliott Bay, the flux of metals from Elliott Bay
shoreline sources was calculated by subtracting the flux of metals out of the
West Duwamish Waterway (Fjjy) from the flux out of Elliott Bay (Fgg)«
Table 11.11 indicates that the Denny Way CSO might contribute 2 to 9% of the
dissolved flux of a metal out of Elliott Bay or 6 to 14% of the dissolved flux
of a metal from shoreline sources. The possible particulate contribution of a
metal from the Denny Way CSO ranged between 4% and 21% of the flux out of
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Elliott Bay. The particulate flux from the CSO could constitute between 9%
and 39% o£ the total shoreline source. Since some metals such as particulate
Pb exhibit higher fluxes in the initial stages of a storm (Dally et al.,
1983), the calculated flux based on one sample collected during the later
stages of the event may be less than the actual flux. From this
order-of-magnitude estimate, it seems that the particulate trace metal
contribution from the CSO is more significant than the dissolved contribution
and that there are other significant shoreline sources. The surface
distribution patterns of the trace metals suggest that the CSO and other
shoreline sources at the north end of Harbor Island were significant inputs to
Elliott Bay during January, 1986. The higher levels of contaminants in the
"hot spot" directly west of the Denny Way CSO (Romberg et al., 1984; Bates
et al., 1987) results from rapid sedimentation of particulates from the
effluent. However, there is little indication that contaminants from "hot
spots", or elsewhere in Elliott Bay, are resuspended, remobilized or
transported out of the Bay.
II.2. COMMENCEMENT BAY
Two moorings, one surface and one subsurface, were centrally located in
the mouth of Commencement Bay to measure currents and water properties at 1,
4, and 152 m in a water depth of 158 m (Table II.1 and Fig. 11.45). This
location was selected because previous water property observations indicated
near surface flow meandering back and forth across the entrance and because
the location was an old dump site of interest. Observations of currents and
shipboard CTD's were obtained over a 21 day period. The CTD observations were
made over a few tidal conditions (Table II.2). The general statistics of the
moored instruments are in Table II.3.
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Figure 11.45. Location of stations and moorings in Commencement Bay. The
station names are derived by adding the prefix 'CB85-' to the station number
shown in the figure. The vertical transect across the heads of the waterways
is composed of stations CB85-1 to CB8S-4. The transect into outer
Commencement Bay is composed of stations CB85-3, CB85-7, -10, -13 and -15.
-152-

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I22°30'
_J	
25'
_L_
47 18'-
RUSTON
COMMENCEMENT BAY
PUYALLUP RIVERH
h47°l8/
I22°30' MIDDLE WATERWAY 25'

-------
11.2.1.	Hydrographic Setting
Puyallup River
The Puyallup River begins at the confluence of the Puyallup and Tacoma
Glaciers on Mount Rainier and flows approximately 46 miles to Commencement
Bay. The river and its principal tributaries (White, Carbon, and Mowich
River) drain approximately 60% of the slopes of Mount Rainier. Two flow
maxima are present during a normal year; high rainfall in winter produces a
December/January peak and snowmelt runoff produces a larger peak in June. The
river flows through forested and agricultural land to the USGS gauging station
near Puyallup. The last 6.6 miles are through urban and industrial areas.
Clear and Clark Creeks enter the river beyond the Puyallup gauging station but
contribute less than 2% of the total river flow (Puget Sound Task Force,
1970).
Mean monthly flow in April 1985 was 133% of the 10-year monthly
average. For the two days of our sampling the flow was 128% of the 10-year
average at a flow rate average of 87 m3/s (Fig. 11.46).
11.2.2.	Physical Oceanography
II.2.2.1. Salinity
Distributions of surface salinity are presented in Fig. 11.47. As in
Elliott Bay, there is a very shallow surface brackish layer, salinity below
the upper few meters is characteristic of the source waters of the main
basin. The major effects of freshening are not obvious below 4 m. The
surface salinity distributions at high tide show weak horizontal gradients,
with slightly less saline water in the northern half of the bay. During ebb
-154-

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the salinity distribution shows much stronger horizontal gradients, and the
plume of fresh water from the Puyallup River exits through the center of the
bay. There is an indication of freshened water coming through Dalco Passage
or from the Narrows.
Salinities measured by the moored instruments show the most variation in
the surface layer (Fig. 11.48). The 1 and 4 m observations indicate how the
extremely thin the layer of fresher water is, much like that in Elliott Bay.
The mean difference is 1.8 ppt with a large variance. There is a trend toward
larger differences through the record, with larger decreases in surface
salinity centered on 3 and 14 April probably due to increased river outflow
(see Fig. 11.46). The Duwamish River has peak flows at about those times.
The patchiness of the fresher water plume also is seen in the salinity
difference series going from almost no difference to large differences. The
difference has variation which does not seem tidal; three peaks/lows are
observed on some days. The salinity gradient is small over the rest of the
water column, increasing by only 1 ppt in 150 m. There is an increase in
bottom salinity in early April. The increase is probably the result of a
bottom water intrusion propagating along the main basin.
II.2.2.2. Currents
The maximum currents at the 4 m and the 152 m level are larger than
currents at similar depths in Elliott Bay (Fig. 11.49). The flow is tidal
with a dominant semi-diurnal component. The cross bay components indicate a
non-zero mean. The low frequency flow (tides removed) also clearly dispLays
this cross bay component (Fig. 11.50), indicating flow at an angle to the
entrance section. Note that there also are uncoupled, alternating periods of
inflow and outflow. The progressive vector diagrams, however, indicate that
-155-

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Figure 11.46, Discharge of the Puyallup River (Upper Figure). Monthly means,
range and standard deviation for the period 1966-1978. Monthly means (Lower
Figure) and range for the period February 1985 - January 1986.
-156-

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PUYALLUP RIVER FLOW (at Puyallup)
500-1
8 400"
300-
y 200
> 100
t*.
10-YEAR AVERAGE
I—I Monthly Range (1966-1978)
I Monthly Standard Deviation
• Monthly Mean
I
5

i
i
t i i i i r
i	r
500 n
8 400-
O 300-
cC.
200-
Sl 100-
YEAR FEBRUARY 1985 - JANUARY 1986
1 . 1 Monthly Range (Feb 85 - Jan 86)
•	Monthly Mean
*	2 Day Sampling Period Mean
~ s
FEB MAR APR MAY JUN JULAUG SEP OCT NOV DEC JAN

-------
Figure 11.47. Distribution of surface salinity in Commencement Bay, March and
April 1985.
-158-

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28.5
29.5
March 25
Higher High Tide
PUYALLUP RIVER"
25'
8505
April I & 2
Higher High Tide
PUYALLUP RIVER"
/
• 27
April 15 %
Higher High Tide
to Ebb
\26
PUYALLUP RIVER

-------
Figure 11.48. Time series of salinity and salinity difference (4 m minus 1 m)
in Commencement Bay. The salinity ranges vary and are scaled to the maximum
and minimum values of the records.
-160-

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30.01
J	i	.	L
_i	i	u
t i
i«2ME-W
20.0 J
^ 31-0 q T l%o
z|29.0;-
—: 290
3 27.0
^ 31.0 q
£ e
— 
-------
Figure 11.49. Time series of currents relative to the axis (315°) of
Commencement Bay. The speed scales vary according to the range of currents
observed.
-162-

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60 -|
1—
(_>
ll i
-
LO
CO
N
0 -
*—4
CO
z:
(_)
_


i
o
o
L.


60 n
(_)
LU
CO
ID
<}•
Lf)
CO
<_)
o
IxJ
CO
152m
/"VlrVl/'
1	1	1	1 I 1	1	1	1	1—
\ fJ p*- f\/\ h r\ 1
i a 1 ¦ i 1 i t. 1 i i ll
vivy \j v yvmk yi|
I 4m
A* AAK+ . A All fl/i^. Im m/i ill
vrnny|
K AaAi/UaJ 1
"«v w* "w ww wu y >\j v/y yy
HaIA aA,A aA/^A jl A/^A j A^oA AjiAa Aa/i Kt
\N' ^ If V w V V1I1|V U V y ||

0
L-60
--AO
yVyw-
85

-------
Figure 11.50. Vector time series of low frequency currents in Commencement
Bay. The vectors are relative to north and scaled to observed minimums and
maximums at 4 and 152 m.
-164-

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0
LU
CO
3.0 3
0
Q_
to
O
-3.0 d
152m
r 3. 0


7|V V
i—
25
Mar
85
27
30
ir
—I	1	r	1	i i	1—
6	9	12
10
-3.0

-------
the net circulation or transport is extremely small (Fig. 11.51). The vector
mean flow values are lower than in Elliott Bay (Fig. II.3.) but the variance
is much greater, particularly at surface, suggesting wind dominated events.
The apparent cross-bay flow at the surface may be a result of different axis
of flow during flood and ebb currents and may not be real. The relatively
short records in Commencement Bay make definitive interpretation difficult.
Water from the Puyallup River mouth would have taken two days to reach Reston
during this period. Near bottom water would have taken 18 days to traverse
the same distance. Nonetheless, it is clear from the coarser bottom sediments
in Commencement Bay that tidal resuspension allows fine particles to diffuse
out of the bay even if advection is very slow.
II.2.3. Particulate Matter Transport
II.2.3.1. SPM - April 1985
The vertical distribution of suspended particulates in Commencement Bay
during April 1-2, 1985 is shown in Figure 11.52.
The highest concentration measured of suspended particulates in
Commencement during April 1-2, 1985 was 2 mg/L at Station 7 near the bottom.
In general, SPM concentrations are highest near the mouth of the Puyallup
River where they increase,with depth (from 1 mg/L at the surface to 2 mg/L at
125 m). The surface concentrations decrease with distance from the river
mouth to -0.6 mg/L in the outer bay surface and intermediate water (Section
b).
A relatively turbid bottom layer about 50 m thick of rather uniform SPM
concentration (-1.5 mg/L) due to tidal sediment resuspension was found from
the Puyallup river mouth throughout the axis of the bay to its confluence with
the main basin of Puget Sound.
-166-

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SPM concentrations along the waterfront of the port facility (Stations
1-4; Section a) were lower at the surface (0.75 mg/L) than at depth
(-1.0 mg/L). The SPM was distributed uniformly horizontally.
II.2.4. Trace Metals and Organics in Commencement Bay
II.2.4.1. Trace Metals
The sampling plan for Commencement Bay included a transect across the
front of the industrial waterways as well as a transect from the Puyallup
Waterway out into Commencement Bay (Fig. 11.45). The data from this transect
were collected in order to evaluate the sources of trace metals to
Commencement Bay. Since all the samples from Commencement Bay were collected
with General Oceanic Go-Flo91 sampling bottles, the vertical resolution of the
data was reduced relative to the small boat sampling data from Elliott Bay.
The samples in the surface plume of the Puyallup River (CB85-2 and CB85-3) had
salinities of 22.65 and 26.04 g/kg, respectively. The surface particulate
samples for the same stations were collected from slightly deeper depths and
had salinities of 29.14 and 29.27 g/kg, respectively. These salinities
indicate that contaminants discharged at the surface would be highly diluted
with cleaner seawater by the time they were mixed down to the depths that were
sampled. The lack of vertical resolution precluded the calculation of
transport out of Commencement Bay by the method described for Elliott Bay.
Iron
The highest concentrations of dissolved Fe (7.6 pg/L) were	found in the
plume of the Puyallup River at stations CB85-2 and CB85-3 (Fig.	11.53).
Concentrations decreased with distance to the side of the plume	and with
-167-

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Figure 11.51. Progressive vector diagrams of currents in Commencement Bay,
April 1985. The scale differences reflect the differences in current
magnitude.
-168-

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+ Every 5 days
-50
-40 -30 -20 -10
K I Iome+ers
+ Every 5 doya
0	5	10
KI Ionetars

-------
Figure 11.52. Vertical Transects of TotaL Suspended Matter in Commencement
Bay. The transect across the heads of the waterways is shown in Fig. a while
the transect that extends into outer Commencement Bay is shown in Fig. b.
-170-

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50-
I
t
UJ
Q
100-
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April 1-2,1985
TOTAL SUSPENDED MATTER
(mg/L)
I	1
I km
150-
13
o

-------
Figure 11.53. Vertical transects of dissolved Fe (a and b) and particulate Fe
(c and d) in Commencement Bay during April, 1985. Transects across the heads
o£ the the waterways (a and c}. Transects into outer Commencement Bay
(b and d).
-172-

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CB85-
1 k
NOAA-EPA
Contaminant Transport Study
L-RERP 8S-2
April 1-2,1985
DISSOLVED Fe (pg/L)
I	1
I km
Q 40"
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April 1-2.1985
PARTICULATE Fe (jig/L)
I	1
I km
r
CB85-

-------
distance out into Commencement Bay. Stations in front of other major
waterways (CB85-1 and CB85-4) had dissolved Fe concentrations only slightly
higher than concentrations in outer Commencement Bay water. There seemed to
be a small secondary plume off the shores of Ruston. Dissolved Fe
concentrations also decreased with depth; values as low as 0.25 ug/L were
found at mid-depth in outer Commencement Bay.
Particulate Fe concentrations were four times higher than dissolved Fe
concentrations in the Puyallup River plume and did not change dramatically to
the sides of the plume nor out into the bay (Fig. 11.53). In contrast,
near-bottom particulate Fe concentrations were 100-300 higher than the
corresponding dissolved concentrations and were 3-4 times higher than
particulate Fe concentrations in the mid-depth region of the water column.
Manganese
The plume of Puyallup River contained the highest concentrations of
dissolved Mn (11.8 ug/L). Surface concentrations to the sides of the plume
and in outer Commencement Bay ranged between 2.1 and 3.3 ug/L (Fig. 11.54).
The increase in dissolved Mn in the bottom waters is probably due to diffusion
of Mn out of the sediments.
Particulate Mn concentrations in the Puyallup River plume were lower than
the dissolved Mn concentrations by about a factor of 5. Concentrations
decreased slightly to the sides of the Puyallup River plume and out into the
Bay (Fig. 11.54). Particulate Mn concentrations increased with depth to
concentrations as high as 4.5 ug/L. In the near-bottom region, particulate Mn
concentrations were generally between 0.5 and 1.0 times the dissolved Mn
concentrations.
-174-

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Copper
The highest concentrations of dissolved Cu (750 ng/L) were found in the
Puyallup River plume and decreased to the sides of the plume and with distance
into outer Commencement Bay (Fig. 11.55). Concentration also decreased with
depth to values less than 300 ng/L in the bottom waters of outer Commencement
Bay.
The highest surface particulate Cu concentration (58 ng/L) was found at
station CB85-4 (near the head of Middle Waterway) with concentrations
decreasing to the northeast and out into the Bay (Fig. 11.55). In the surface
waters of Commencement Bay, particulate Cu concentrations were usually less
than one-tenth of the dissolved Cu concentrations. A secondary particulate Cu
plume was aLso observed off the shores of Ruston. Particulate Cu
concentrations increased in the near-bottom nepheloid layer by a factor of
about 3 relative to mid-depth concentrations. In the near-bottom region,
dissolved Cu concentrations were greater than particulate Cu concentrations by
factors ranging between 3 and 6.
Zinc
The highest dissolved Zn concentration of 2600 ng/L was found in the
plume of the Puyallup River. Concentration decreased to 1100 ng/L to sides of
the plume and out into the Bay (Fig. 11.56). A secondary plume was evident
off the shores of Ruston. Dissolved Zn concentrations decrease with depth to
values Less than 700 ng/L in the bottom waters of outer Commencement Bay.
The highest surface particulate Zn concentration (155 ng/L) was also
found in the Puyallup River plume (Fig. 11.56), although it was 10 cimes lower
than the corresponding dissolved Zn concentration. The surface particulate Zn
concentrations decreased both to the sides of the plume and oue into the
-175-

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Figure 11.54. Vertical transects of dissolved Mn (a and b) and particulate Mn
(c and d) in Commencement Bay during April, 1985. Transects across the heads
of the the waterways (a and c). Transects into outer Commencement Bay
(b and d).
-176-

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CB85-
NOAA-EPA
Contaminant Transport Study
L-RERP 65-2
April 1-2,1985
DISSOLVED Mn (yg/L)
h
Ikm
CB85-
Q 40"
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April 1-2,1985
PARTICULATE Mn (vig/L)
I	1
I km
CB85-

-------
Figure 11.55. Vertical transects of dissolved Cu (a and b) and particulate Cu
(c and d) in Commencement Bay during April, 1985. Transects across the heads
of the the waterways (a and c). Transects into outer Commencement Bay
(b and d).
-178-

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C88S-
I I /WW r
E 20-
CB85-
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April 1-2,1985
DISSOLVED Cu (ng/L)
(km
CB85-

Q 40"
CB85-
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April 1-2,1985
PARTICULATE Cu (ng/L)
I	1
I km


-------
Figure 11.56. Vertical transects o£ dissolved Zn (a and b) and particulate Zn
(c and d) in Commencement Bay during April, 1985. Transects across the heads
of the Che waterways (a and c). Transects into outer Commencement Bay
(b and d).
-180-

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T5fSSSi
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April 1-2,1985
DISSOLVED Zn (ng/L)
I	1
I km
2500
50-
I
£
100-
150-
CB85-
13
IS
-1500-
1000-


100 __
1 20-
Q 40"
CB85-
3 7
50-
£
X
fc
LU
Q
100-
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April l-Z 1985
PARTICULATE Zn (ng/L)
I km
150-
10
13
15
1 • / •
•j ¦ •
4 I / #
© ¦
vk* \\
A T\foo
/•
\ \ ,5°\

A 200 \
V V
V • /
\*300


mTt>w •

-------
Bay. The particulate Zn concentrations increased with depth to values as high
as 315 ng/L in the near-bottom nepheloid layer of outer Commencement Bay. In
this region, the particulate Zn concentrations were between 0.25 and 0.5 times
the corresponding dissolved Zn.
Lead
The highest concentration of dissolved Pb (80 ng/L) was found in the
plume of the Puyallup River and values decreased to the side of the plume
(Fig. 11.57). Dissolved Pb concentrations also decreased with distance into
the Bay. Dissolved Pb concentrations decreased with depth to values less than
10 ng/L in the bottom water of outer Commencement Bay.
The concentration of particulate Pb in the Puyallup River Plume was
202 ng/L (Fig. 11.57) which was more than twice the dissolved Pb
concentration. Although the particulate Pb concentrations in surface waters
decreased to the side of the plume, the concentrations in front of the other
waterways were greater than concentrations in the outer Bay. In outer
Commencement Bay, the particulate Pb concentrations increase in the
near-bottom nepheloid layer to values 2 to 4 times higher than mid-depth
concentrations. The particulate Pb concentrations in the nepheloid Layer were
more than 5 times the corresponding dissolved Pb concentrations.
Nickel
The transect of dissolved Ni showed the least variation of the metals
studied in Commencement Bay (Fig. 11.58). Dissolved Ni only varied between
570 ng/L in the river plume and 390 ng/L in the bottom waters of outer
Commencement Bay.
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The particulate Ni concentration in the Puyallup River Plume was 25 ng/L
(Fig. 11.58) which was 20 times lower than the dissolved Ni concentrations.
Surface particulate Ni concentrations decreased to the side of the plume and
out into the Bay. The particulate Ni concentrations in the near-bottom layer
were higher than mid-depth stations by factors ranging between 2 and 3. In
the nepheloid layer, the dissolved Ni concentrations were still greater than
the particulate Ni concentrations by factors greater than 5.
Cadmium
As in Elliott Bay, the lowest dissolved Cd concentration (75 ng/L) was
found in the river plume (Fig. 11.59). However, surface concentrations from
other samples collected at the head of other waterways were slightly higher
than the concentrations of offshore waters.
Chromium
The surface particulate Cr concentration in the Puyallup River plume
(52 ng/L) was only slightly higher than concentrations in surface waters to
the side of the plume and in outer Commencement Bay. Particulate Cr
concentrations in the nepheloid layer were 2 to 5 times higher than mid-depth
concentrations.
II.2.4.2. Toxic Organics
Commencement Bay PAH concentrations in April 1985 were 3.5 ug/g in the
surface waters and 2.0 vig/g at 20 m (Fig. 11.60). The concentration at the
lower depth compares well with the concentration of 2.2 ug/g found on settling
particulates at the same depth in May of 1981 (Bates et al., 1987).
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Figure 11.57. Vertical transects of dissolved Pb (a and b) and particulate Pb
(c and d) in Commencement Bay during April, 1985. Transects across the heads
of the the waterways (a and c). Transects into outer Commencement Bay
(b and d).
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CB85-


NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April 1-2,1985
DISSOLVED Pb (ng/L)
I km
CB85-

loo-:
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April 1-2,1985
PARTICULATE Pb (ng/L)
(km
CB85-

-------
Figure 11.58. Vertical transects of dissolved Ni (a and b) and particulate Ni
(c and d) in Commencement Bay during April, 1985. Transects across the heads
of the the waterways (a and c). Transects into outer Commencement Bay
(b and d).
-186-

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NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April 1-2,1985
DISSOLVED Ni (ng/L)
I	1
I km

CB85-
J 20-
O 40-
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April 1-2.1985
PARTICULATE Ni (ng/L)
h
Ikm
CB8S-

-------
Figure 11.59. Vertical transects of dissolved Cd (a and b) Commencement Bay
during April, 1985. The transect across the heads of the the waterways is
depicted in Figs, a while the transect into outer Commencement Bay is shown in
Figs. b.
-188-

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CB85-
50-
n
h-
a.
100-I
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April 1-2, 1985
DISSOLVED Cd (ng/L)
I	1	150 H
I km

-------
gure 11.60. PAH in Commencement Bay.
-190-

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PAH CONCENTRATIONS IN COMMENCEMENT BAY (ng/g)
47 18'-
4000-1
3000-
2000-
1000 -
NOAA-EPA
Contaminant Transport Study
L-RERP 85-2
April 4-5, 1985
PUYALLUP RIVER-*W	
W"
122 30
S Surface
A April
ST Sediment Trap
S 20m
A6
150m
ST 7
20 120m
ST 8

-------
Polychlorinated biphenyl concentrations in Commencement Bay were near or
below our detection limits. DDT, DDE and DDD were all below detection
limits. Since widespread use of these chlorinated hydrocarbons was curtailed
in the 1970'3, the low concentrations we observe are not surprising.
II.2.4.3. Summary
The major source of both dissolved and particulate metals discharged into
Commencement Bay clearly is the Puyallup River plume. Whether this source
originates from the Puyallup River itself or entrained from anthropogenic
sources on the Commencement Bay waterfront can not be determined from this
study. While particulate Fe and Pb are the dominant forms of these trace
metals in the plume, dissolved Mn, Cu, Zn and Ni predominate. The surface
concentration of most metals decreases to the sides of the plume and with
distance into the outer Bay. This decrease is a result of dilution by deeper,
more-saline water which has lower metal concentrations. The distribution of
particulate and dissolved metals in the water column is distinctly
different. For dissoLved metals, only dissolved Mn shows any indication of a
significant increase near the bottom. In contrast, the presence of a
near-bottom nepheloid layer containing a large particulate concentration
results in near-bottom maximums for all particulate metals. This behavior
shifts the partitioning of all metals towards the particulate phase.
The low PAH concentrations on settling particulates in Commencement Bay
are consistent with the low values on surface sediments in the deeper waters
of Commencement Bay (Crecelius et al., 1983). The strong currents in
Commencement Bay prevent the accumulation of fine-grained sediment and their
associated PAH. The suspended PAH in Commencement Bay are likely transported
out of the Bay, through Colvos Passage and ultimately deposited in the
-192-

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sediments of the central Main Basin (Bates et al., 1987). The small amounts
of PCB present presumably result from scouring of pipes in which PCB compounds
were previously deposited and perhaps from dredging and relocation of PCB-
contaminated sediments.
-193-

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III. REFERENCES
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Rep. ERL 417-PMEL 35, 44 pp.
Baker, E.T., and J.W. Lavelle, (1985). The effect of particle size on the
light attenuation coefficient of natural suspensions. Journal of
Geophysical Research 89: C5, 8197-8203.
Baker, E.T., and H.B. Milburn (1983). An instrument system for the
investigation of particle fluxes. Cont. Shelf. Res. 1, 425-435.
Baker, E.T., Cannon, G.A. and Curl, H.C. Jr., (1983). Particle transport
processes in a small marine bay. Journal of Geophysical Research 88'.
9661-9969.
Barrick, R.C. (1982). Flux of Aliphatic and Polycyclic Aromatic Hydrocarbons
to Central Puget Sound from Seattle (Westpoint) Primary Sewage Effluent.
Environmental Science and Technology 16: 682-692.
Bates, T.S., S.E. Hamilton, and J.D. Cline (1984). Vertical Transport and
Sedimentation of Hydrocarbons in the Central Main Basin of Puget Sound,
Washington. Environmental Science and Technology 18: 299-305.
Bates, T.S., P.P. Murphy, H.C. Curl, Jr., and R.A. Feely (1987). Hydrocarbon
distribution and transport in an urban estuary. Environmental Science and
Technology, in press.
Boyle, E.A., J.M. Edmonds, and E.R. Sholkovitz, (1977). The mechanism of iron
removal in estuaries. Geochimica et Cosmochimica Acta 41'. 1313-1324.
Boyle, E.A., R. Collier, A.T. Oengler, J.M. Edmond, A.C. Ng, and R.F.
Stallard, (1974). On the chemical mass-balance in estuaries. Geochim.
Cosmochim. Acta 38, 1719-1728.
-194-

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Cairns, T. and E.G. Siegmund (1981). PCBs: Regulatory History and Analytical
Problems. Analytical Chemistry 53: 1183A-1193A.
Cannon, G.A., and Grigsby, M.W., (1982). Observations of currents and water
properties in Commencement Bay. NOAA Technical Memorandum OMPA-22,
Boulder, CO, 35 pp.
Crecelius, E.A., R.G. Riley, N.S. Bloom, and B.L. Thomas (1983). History of
contamination of sediments in Commencement Bay, Tacoma, Washington. NOAA
Technical Memorandum OMPA 20.
Curl, H.C., Jr., C.T. Baker, T. Bates, G. Cannon, J. Cline, E.D. Cokelet, S.
Hamilton, R.A. Feely, M. Lamb, J.W. Lavelle, G.J. Massoth, H.O. Mofjeld,
J.W. Murray, A.J. Paulson and R.J. Stewart., (1982). Estuarine and
coastal poLlutant transport and transformation: The role of
particulates. Pacific Marine Environmental Laboratory, Seattle, WA.
Dally, L.K., D.P. Lettenmaier, S.J. Burges, and M.M. Benjamin (1983).
Operation of detention facilities for urban stream quality enhancement,
Water Resources Series Technical Report JVo, 79, Department of Civil
Engineering, University of Washington, Seattle, WA.
Eganhouse, R.P. and I.R. Kaplan (1931). Extractable Organic Matter in Urban
Stormwater Runoff. 1. Transport Dynamics and Mass Emission Rates.
Environmental Science nd Technology 15: 310-315.
Evans-Hamilton, Inc. (1986). Puget Sound Environmental Atlas.
Feely, R.A., Massoth, G.J., Paulson, A.J. and Gendron, J.F., (1983). Possible
evidence for enrichment of trace elements in the hydrous manganese oxide
phases of suspended matter from an urbanized embayment. Estuarine,
Coastal and Shelf Science 17: 693-708.
Feely, R.A., G.J. Massoth, E.T. Baker, J.F. Gendron and A.J. Paulson,
(1986). Seasonal and vertical variations in the elemental composition of
-195-

-------
suspended and settling particulate matter in Puget Sound, Washington.
Estuarine, Coastal and Shelf Science 22: 215-239.
Gamponia, V., T. Hubbard, P. Romberg, T. Sample, and R. Swartz (1986).
Identifying hot spots in the lower Duwamish River using sediment chemistry
and distribution patterns. Water Quality Planning Division, Municipality
of Metropolitan Seattle, WA.
Hafferty, A.S., S.P. Pavlou and W. Horn (1977). Release of polychlorinated
biphenyls (PCS) in a salt wedge estuary as induced by dredging of
contaminated sediments. Science of the Total Environment 8: 229-239.
Hamilton, S.E., T.S. Bates, and J.D. Cline (1984). Sources and Transport of
Hydrocarbons in the Green-Duwamish River, Washington. Environmental
Science and Technology 18i 72-79.
Harper-Owes (1983). Water quality assessment of the Duwamish Estuary,
Washington. Municipality of Metropolitan Seattle, WA, 193 p.
Lake, J.L., C. Norwood, C. Dimock, and R, Bowen (1979). Origins of polycyclic
aromatic hydrocarbons in estuarine sediments. Geochimica et Cosmochimica
Acta 43: 1847-1854.
Liss, P.S., (1976). Conservative and non-conservative behavior of dissoLved
constituents during estuarine mixing. IN: Estuarine Chemistry (Burton
J.D. and Lisi P.S., editors). Academic Press, New York.
NOAA National Weather Service. Local Climatological Data Monthly Summary.
Paulson, A.J., R.A. Feely, H.C. Curl, Jr., and J.F. Gendron, (1984). Behavior
of Fe, Mn, Cu and Cd in the Duwamish River estuary downstream of a sewage
treatment plan. Wat. Res. 18, 633-641.
Puget Sound Task Force of the Pacific Northwest River Basins Commission
(1970). Comprehensive Study of Water and Related Land Resources: Puget
Sound and Adjacent Waters.
-196-

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Romberg, G.P., S.P. PavLou, R.F. Shok.es, M. Horn, E.A. Crecelius, P. Hamilton,
J.T. Gunn, R.D. Muench, and J. Vinelli (1984). Toxicant Pretreatment
Planning Study Technical Report CI: Presence, Distribution and Fate of
Toxicants in Puget Sound and Lake Washington.
Sackett, W.M. and G. Arrhenius (1962). Distribution of aluminum species in
the hydrosphere: 1. Aluminum in the oceans. Geochim Cosmochim Acta 26:
955-968.
Santos, J.F. and J.D. Stoner (1982). Physical, chemical, and biological
aspects of the Duwamish River Estuary, King County, Washington 1963-67.
Geological Survey Water-Supply Paper 1873-C, U.S. Gov. Print. Off.,
Washington, D.C., 74 p.
Sillcox, R.L., Geyer, W.R. and Cannon, G.A., (1981). Physical transport
processes and circulation in Elliott Bay. NOAA Technical Memorandum OMPA-
8, Boulder, CO, 45 pp.
Tetra Tech, Inc. (1986). Elliott Bay Toxics Action Program: Initial Data
Summaries and Problem Identification.
Tomlinson, R.D., B.N. Bebee, S. Lazoff, D.E. Spyridakis, M.F. Shepard, R.M.
Thom, K.K. Chew and R.R. Whitney (1980). Fate and effects of particulates
discharged by combined sewers and storm drains. U.S. E.P.A. (600/2—80—
111), Cincinnaci, OH, 164 p.
Zawlocki, K.R. (1981). A survey of trace organics in highway runoff in
Seattle, Washington. M. Sc. Thesis, University of Washington, SeattLe.
-197-

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APPENDIX I.	PARTICULATE CHEMISTRY DATA FDR ELLIOTT BAY
(in uiits of wt./vol. of water)
L-REEP 85-2, April 4-5, 1985


Position
Depth Sal
191
A1
Ti
Or
Ma
Fe
Ni
Cu
Zn
Pb
Station Date/Time
N/W
m
g/kg
yg/L
yg/i<
Vg/L
ng/L
vg/L
Ug/L
ng/L ng/L ng/L
ng/L
EB85-1
4APR85/1506
47°35.80/122°20.65
2
23.61
945.8
80.2
5.05
77
2.23
58.7
30
60
232
78



10
29.74
32D.7
20.5
1.16
21
1.51
13.3
10
9
50
42



20
29.80
373.5
22.3
1.53
26
2.31
16.7
14
16
82
41



50
29.94
491.5
33-3
2.17
34
2.85
22.7
20
30
118
49
EE85-2
UAPR85/1525
47o36^3/122°20.55
2
29.38
515.4
33.6
222
36
1.34
26.6
18
55
111
66



10
29.75
301.0
19.3
1.19
23
1.67
13.4
11
16
64
37



20
29.77
354.3
19.1
1.21
22
2.04
13.3
11
13
77
41



60
29.96
460.6
33.8
2.14
36
2.83
22.4
22
29
84
49
EB85-3
4APR85/0858
47°35.57/122°21.55
2
28.62
887.6
67.7
5.19
80
2.01
60.3
35
204
229
97



10
29.74
260.0
16.2
1.04
19
1.69
11.4
10
7
60
28



20
29.79
273.1
13-9
1.09
19
1.47
11.7
11
11
58
24



50
30.05
426.6
31.8
1.93
31
2.62
19.7
20
16
61
32
EB85-4
4APR35/1033
47°35.8Q/122°21.90
2
27.74
1240.0
98.2
6.99
97
2.52
83.6
42
95
227
101



10
29.56
307.2
15.8
1.14
18
1.12
13.5
9
15
70
23



20
29.80
342.2
19.8
1.43
24
2.07
15.5
14
12
65
45



40
29.94
42T.2
25.8
1.73
30
2.67
18.3
17
18
106
34



65
30.00
391.1
32.7
2.09
34
3.94
21.5
21
18
70
42
EB85-5
UAPRS5/1139
47°36.27/122°21.30
10
27.08
1422.7
116.1
8.04
106
2.50
99.4
48
92
213
112



20
29.76
304.5
18.6
1.17
20
1.84
13.5
10
10
90
37



40
29.95
416.5
26.3
1.68
29
2.82
18.2
17
12
148
50



60
30.06
391.8
26.1
1.53
26
2.47
16.6
14
4
79
27



90
30.10
483.1
37.3
2.16
37
3.16
22.3
23
19
89
42
EB85-6
4APR85/14G5
47°36.70/122°21.58
2
25.98* 2347.9
237.6
13.79
186
3.92
171.0
87
171
456
146



10
29.74*
259.9
15.3
0.92
17
0.88
10.4
8
3
36
28



40
29.88*
647.1
46.4
3.16
54
3.29
33.0
33
74
142
94



60
30.05
639.2
41.2
2.82
45
3.29
29.7
28
40
142
44
EB85-7
5APR85/1451
47°37X»2/122°21.73
2
29.02* 1010.2
87.9
6.02
76
1.97
66.6
35
64
186
80



10
29.71*
389.2
22.7
1.71
25
1.44
18.5
12
17
69
81



30
29.86
424.5
27.8
1.71
30
2.70
18.3
15
17
80
36
EB85-8
4APR85/1741
47°36.08/122°23.07
10
29.31*
386.1
22.8
1.40
42
1.69
15.8
37
56
48
47



40
29.96
362.0
26.7
1.61
29
2.51
16.6
16
24
54
38
•Salinity calculated from CTD data vhila ,ample was being collected.
-198-

-------
APPENDIX I. (Continued)	PARTICULATE CHEMISTRY DATA FOR ELLIOTT BAY
(in uiits of wt./vol. of water)
L-RERP 85-2, April 4-5, 1985

Position
Depth
Sal
T34
A1
Ti
Cr
Mi
Fe
Ni
Cu
Zn
Pb
Station Date/Time
N/W
m
g/kg
Ug/L
Ug/L
ug/L
ng/L
Ug/L
Ug/L
ng/L ng/L
ng/L
ng/L
EB85-9 4APR85/1257
47°36.73/122°22.92
2
27.60
1338.6
118.1
7.68
107
2.68
93.1
46
91
220
60


20
29.83
261.6
17.8
0.84
**
1.65
9.3
7
**
30
**


40
29.96
372.1
25.5
1.59
26
2.47
16.2
15
14
67
44


60
30.03
361.0
25.2
1.49
26
2.28
15.5
15
11
83
34


100
30.22
804.1
61.7
4.25
66
3.45
44.4
42
59
130
88


150
30.34
856.5
66.8
4.57
69
3.01
45.9
46
53
131
81
EB85-10 5APR85/1159
47°37.27/122°22.83
2
26.48*
2267.1
207.0
14.47
167
3.84
160.5
78
171
316
122


20
29.77*
378.8
22.4
1.26
29
1.72
13.6
14
10
43
30


40
30.05
369.1
28.4
1.50
25
1.49
16.0
14
13
66
41
EB85-11 4APR85/2101
47°35.2B/122°24.70
2
29.77*
471.3
30.3
1.60
27
2.03
17.1
14
8
88
25


20
29.80*
499.4
30.5
1.81
30
2.26
18.7
15
10
66
35


40
29.86*
529.3
40.4
2.18
36
2.63
22.3
21
19
67
39


70
30.19
809.8
50.3
3.68
55
3.12
36.0
35
38
106
56
EB85-12 4APR85/1806
47°35.98/122°24.77
SFC
29.73*
481.3
27.6
1.70
29
1.82
18.1
15
10
62
33


160
30.49
2040.2
95.7
9.81
140
4.34
62.5
98
141
264
125
EB85-13 4APR85/1702
47°36.70/122°24.77
2
28.79*
650.5
58.7
3.59
53
1.89
43.5
24
35
112
66


20
29.81*
395.0
25.0
1.56
26
2.43
16.6
14
14
62
34


40
29.91*
320.3
22.0
1.48
26
2.31
15.0
14
16
56
41


60
30.03*
328.4
19.3
1.26
23
1.63
12.6
12
11
48
34


100
30.22*
509.4
32.7
2.36
39
2.65
23.4
23
20
84
37


180
30.53
442.4
35.6
1.81
33
2.26
19.4
19
58
86
50
EB85-14 5APR85/1423
47°37.53/122°24.68
2
27.45*
2451.6
211.1
15.59
182
4.24
138.6
88
190
365
146


20
29.81*
365.9
24.4
1.48
25
2.13
15.9
14
11
63
45


40
29.93*
376.3
29.0
1.70
30
2.70
17.5
17
16
64
32


60
29.97*
437.1
29.9
1.77
30
2.61
18.2
18
21
71
48


80
30.39
1401.0
77.6
6.56
99
3.40
63.4
64
78
170
82
"Salinity calculated frxm CTD data while sample was being collected.
**Below Detection Limits
-199-

-------
APPENDIX I. (Continued)	PARTICULATE CHEMISTRY DATA FOR ELLIOTT BAY
Snail Boat
(in units of wt./vol. of water)
L-REHP 85-2, April 4-5, 1986


Position
Depth Sal
TSM
A1
TL
Cr
Ml
Fe
Ni
Cu
Zn
Pb
Station Date/Time
N/W
m
g/kg
Ug/L
ug/L
yg/L
ng/L ug/L
yg/L
ng/L ng/L ng/L
ng/L
EB85-SB1
4Apr85/1038
47°35.96/122°20.43
SFC
20.84
3312.8
322.2
20843
464
5.60
278.9
131
392
565
244
EB85-S2
4Apr85/1246
47°36.31/122°20.71
3C
18.44
3495.4
290.6
22337
449
5.58
278.0
145
335
520
195
EB85-SB3
4Apr85/1019
47°35.42/122°21.53
SPC
9.62
8564.3
586.1
51766 1041 12.88
633.6
334
838
1261
475
EB85-S4
4Apr85/1047
47°35.90/122°21.63
SFC
14.46
7525.0
606.8
48419
967 12.01
595.5
288
877
1257
472
EB85-SB5
4Apr85/123B
47°36.30/122°21.67
SFC
18.43
4861.9
320.9
32054
670
8.34
322.9
197
578
952
352
EB85-SB6
4Apr85/1257
47°36.72/122°21.06
SPC
19.31
4216.7
3^7.3
26988
576
7.00
350.4
160
454
754
265
EB85-SB7
4Apr85/1408
47°37.26/122°22.22
SFC
19.91
3941.5
313.0
25613
548
0.72
334.9
159
428
735
272
EB85-SB8
4Apr85/1224
47°35.97/122°23.20
SPC
23.02
1005.0
80.3
5647
127
2.21
72.3
35
144
224
205
EB85-SB9
4Apr85/13l6
47°36.70/122°22.95
SFC
23.20
2971.7
234.5
19330
401
5.16
247.4
122
354
515
207
EB85-SB10
4Apr85/l425
47°37.40/122°23.22
SPC
20.62
2937.9
218.6
18446
407
5.22
255.6
126
370
742
234
EB85-SB13
4Apr85/1343
47°36.80/122°24.66
SFC
24.29
2155.1
178.5
1537
284
3.77
171.6
86
224
3m
148
EB85-SB14
4Apr85/l439
47°38.17/122°24.88
SFC
21.46
2658.0
207.0
17274
393
4.68
230.5
125
348
551
424
EB85-SBDR0
4Apr85/09l8
47°35.01/122°21.54
SFC
8.39
10644.1
622.1
66752 1381 16.98
821.7
459
1127
1456
633
EB85-SBT1
4Apn85/0608
47°35.41/122°22.52
SPC
***
1061.5
44.2
6967
203
2.82
75.1
42
223
229
278
EB85-SETT8
4Apr85/1333
47°36.79/122°24.58
SFC
29.33
407.5
23.7
12985
32
1.03
17.9
[2]
15
22 [49]
EB85-SBT9
4Apr85/1349
47°37.12/122°24.67
SPC
24.87
2425.0
207.0
15146
333
4.38
196.7
109
291
475
415
EB85-SBT13
4Apr85/l449
48°38.19/122°25.51
SFC
25.95
1440.0
130.0
8012
180
2.61
109.9
50
143
251
134
EB85-SBT14
4Apr85/1501
47°38.56/122°25.60
SPC
22.04
in
&
283.2
21855
500
5.96
299.6
172
430
680
394
***ffot Reported
The Fe values for stations EB85-33DR0 and EB85-SB3 were calculated fl-cm the K2 peak.
-200-

-------
APPENDIX II.	PARTICULATE CHEMISTRY DATA FOR ELLIOTT BAY
(in units of wt./wt. of suspended matter)
L-REHP 85-2, April 4-5, 1986


Position Depth
Sal
131
A1
Ti
Cr
Ml
Fe
Ni
Cu
Zn
Pb
Station Date/Time
N/W
m
g/kg
yg/L
*
*
ppm
PPm
f
ppm
ppm
ppm
ppm
EB85-1
4APR85/1506
47°35.80/122
-------
APPENDIX II. (Continued)	PARTICULATE CHEMISTRY DATA FDR ELLIOTT BAX
(in in its of wt./wt. of suspended natter)
L-RERP 85-2, April 4-5, 1986

Position Depth
Sal
121
A1
TL
Cr
Ma
Fe
Ni
Cu
Zn
Pb
Station Date/Time
N/W
m
g/kg
Ug/L
%
%
ppm
ppn
%
ppm
pan
ppm
ppm
EE85-9 4APR85/1257
47°36.73/122°22.92
2
27.60
1388.6
8.51
0.55
77
1929
6.71
33
65
158
43


20
29.83
251.6
6.80
0.32
**
6299
3.54
25
**
116
**


40
29.96
372.1
6.86
0.43
70
6636
4.36
40
36
180
119


60
30.03
361.0
7.26
0.41
72
6316
4.28
42
31
229
94


100
30.22
804.1
7.67
0.53
82
4294
5.52
52
73
162
109


150
30.34
856.5
7.79
0.53
81
3592
5.36
53
62
152
94
EB85-10 5APR85/1159
47037.27/122°22.83
2
25.48*
2267.1
9.13
0.64
74
1695
7.08
35
75
140
54


20
29.77*
378.8
5.90
0.33
76
4528
3.59
36
27
113
79


40
30.05
369.1
7.70
0.41
67
4045
4.32
38
34
178
111
EB85-11 4APR85/2101
47°35.28/122°24.70
2
29.77*
471.3
6.44
0.34
57
4302
3.63
30
17
186
53


20
29.80*
499.4
6.11
0.36
61
4529
3.74
31
21
131
71


40
29.86*
529.3
7.63
0.41
67
4964
4.21
40
36
126
74


70
30.19
809.8
6.21
0.45
68
3854
4.44
44
47
131
69
EB85-12 4APR85/1806
47°35.98/122*24.77
arc
29.73*
481.3
5.73
0.35
60
3789
3.77
32
20
129
68


160
30.49
2040.2
4.69
0.48
69
2126
3.06
48
69
129
61
EB85-13 4APR85/1702
47°36.70/122°24.77
2
28.79*
650.5
9.03
0.55
81
2906
6.68
36
54
172
101


20
29.81*
395.0
6.32
0.40
66
6148
4.19
36
35
157
85


40
29.91*
320.3
6.88
0.46
82
7214
4.67
45
50
174
128


60
30.03*
323.4
5.87
0.39
70
4968
3.84
36
34
147
102


100
30.22*
509.4
6.42
0.46
77
5197
4.59
45
39
164
73


180
30.53
442.4
8.06
0.41
74
5117
4.37
42
130
195
113
EB85-14 5APR85/1423
47037.53/122o24.68
2
27.45*
2451.6
8.61
0.64
74
1727
5.65
36
77
149
59


20
29.81*
365.9
6.68
0.40
71
5828
4.33
37
31
172
123


40
29.93*
376.3
7.72
0.45
79
7167
4.64
44
41
171
84


60
29.97*
437.1
6.84
0.41
68
6057
4.16
40
48
163
110


80
30.39
1401.0
5.54
0.47
70
2424
4.52
45
56
121
65
•Salinity calculated from CTD data vtfiile sanple was being collected.
**Below Detection Limits
-202-

-------
APPENDIX II. (Continued)	PARTICULATE CHEMISTRY DATA FDR ELLIOTT BAY
Small Boat
(in units of wt./wt. of suspended matter)
L-RERP 85-2, April 4-5, 1985


Position
Depth Sal
T3<
A1
n
Cr
Ml
Ete
Ni
Cu
Zn
Pb
Station
Date/Time
N/W
m
g/kg
yg/L
%
*
PPn
ppra
%
pprn
ppm
ppn
ppm
EB85-SB1
4APR85/1033
47°35.96/122<>20.43
SC
20.84
3312.8
9.72
6292
140
1689
8.42
40
118
171
74
EB85-SB2
4APR85/12U6
U7°36.31/122°20.71
SC
18.44
3495.4
8.31
6405
123
1598
7.95
41
96
149
56
EB85-SB3
4APR85/1019
47°35.42/122°21.53
SFC
9.62
8564.3
6.84
6044
122
1504
7.42
39
98
147
55
EE85-SB4
4APR85/1047
47°35.9Q/122°21 .63
SC
14.46
7525.0
8.06
6434
128
1596
7.91
38
117
167
63
EB85-SB5
4APR85/1238
47°36.30/122°21.67
SFC
18.43
4861.9
6.60
6593
138
1715
6.64
41
119
196
72
EB85-SB6
4APR85/1257
47°36.72/122°21.06
sec
19.31
4216.7
8.24
6400
137
1661
8.31
38
108
179
63
EB85-SB7
4APR85/1408
4
O
5
o
p
IS
arc
19.91
3941.5
7.94
6498
139
1705
8.50
40
109
186
69
EB85-SB8
4APR85/1224
47°35.97/122°23.20
SPC
23.02
1005.0
7.98
5619
127
2195
7.19
35
144
222
204
EB85-SB9
4APR85/1316
M7°36.70/122°22.95
SFC
23.20
2971.7
7.89
6505
135
1737
8.33
41
119
173
70
EB85-SB10
4APR85/1425
^7°37.40/122°23.22
SPC
20.62
2937.9
7.44
6279
138
1777
8.70
43
126
252
80
EB85-SB13
4APR85/1343
47°36.80/122°24.66
SFC
24.29
2155.1
5.82
3771
79
2535
4.40
**
3J
54
121
EB85-SB14
4APR85/1439
47°33.17/122°24.88
sc
21.46
2658.0
7.79
6499
148
1761
8.67
47
131
207
159
EB85-SEDR0
4APR85/0918
47°35.01/122°21.54
SFC
8.39
10644.1
5.84
6271
130
1595
7.72
43
106
137
59
EB85-SBT1
4APR85/06Q8
47°35.41 /122°22.52
SE
u u u
1061.5
4.16
6563
192
2651
7.07
40
210
216
262
EB85-SBT8
4APR85/1333
47°36.79/122»24.58
SFC
29.33
407.5
8.a3
6025
132
1751
7.96
40
104
162
68
EB85-SBT9
4APR85/1349
47°37.12/122°24.67
SPC
24.87
2425.0
8.54
6246
137
1807
8.11
45
120
196
171
EB85-SBT13
4APR85/1449
48°38.19/122°25.51
SFC
25.95
1440.0
9.03
5564
125
1809
7.63
34
99
174
93
EB85-SBT14
4APR85/1501
47°38 -56/122°25.60
SPC
22.04
343TT.5
8.24
6358
145
1732
8.71
50
125
198
115
**Below Detection Limits
***Not Reported
Hie Fe values for stations EB85-SBDR0 and EB85-SB3 were calculated using the K2 peak.
-203-

-------
APPENDIX III.
PARTICULATE CHEMISTRY DATA FDR EXLIOTT BAY
(in uiits of wt./vol. of water)
L-RERP 86-1, Jaiuary 8, 9, and 23, 1986


Position
Depth Sal
T34
A1
n
Cr
Ma
Fe
Ni
Qi
Zn
Pb
Station Date/Time
N/W
m

Vg/L
Ug'L
Ug/L
ng/L
ng/L
Ug/L
ng/L
ng/L
ng/L
ng/L
SI
8JAN86/0840
47°37.1/122°21.6
SC
20.40 36000.0
844
75.78
1444
12080
845.3
1023
6608
14504
10155
S2
8JAN86/0855
47°36.9/122°22.0
SFC
28.61
1876.7
134
7.20
151
2562
95.8
86
194
295
448
S3
8JAN86/0924
47°36.6/122°22.4
src
29.99
792.0
72
3.32
61
3441
36.8
34
15
165
116
S3
&JAN86/0924
47°36.6/122°22.4
3"C
29.99
792.0
65
3.61
64
3757
39.9
33
30
152
124
S4
8JAN86/0946
47°36.5/122°23.3
src
30.19
760.0
54
2.47
44
3620
26.3
30
**
119
44
S5
8JAN86/1021
47°37.2/122°23.1
src
29.01
1290.0
110
5.40
107
2836
76.5
56
112
241
295
S5
8JAN86/1021
47°37.2/122°23.1
src
29.01
1290.0
110
5.22
95
2737
73.6
57
121
246
254
S6
8JAN86/1045
47°37.2/122°22.7
src
29.22
1250.6
100
5.41
104
3135
71.7
46
198
267
251
S6
8JAN86/1045
47°3T.2/122°22.7
sc
29.22
1250.6
104
5.31
108
3090
71.1
52
162
2T0
245
S7
8JAN86/1105
47°37.6/122°22.7
src
27.36
1913.3
132
7.08
148
2737
105.7
78
339
579
596
S8
8JAN86/1126
47°37.6/122°22.1
src
27.92
4016.7
225
16.58
25
3358
185.3
196
178
427
336
S8
8JAN86/1126
47°37.6/122°22.1
SFC
27.92
3420.0
237
15.50
289
4133
184.9
210
**
357
346
S9
8JAN86/1256
47°37.5/122°23.2
SEC
27.79
2330.0
170
9.17
164
3134
127.3
96
229
585
579
S10
8JAN86/1307
47°37.2/122°23.3
src
27.75
1403.3
105
5.58
108
2594
75.3
56
151
327
470
S11
8JAN86/1320
47°36.9/122°23.5
src
29.94
796.0
57
3.17
47
3511
34.0
24
11
127
90
S12
8JAN86/1331
47°36.7/122°23.3
src
30.04
704.0
53
2.54
53
3448
29.0
22
2
111
90
SI 3
8JAN86/1400
47°36.8/122°23.7
src
30.00
658.0
41
2.49
3B
2951
25.5
22
**
149
94
S14
8JAN86/1411
47°38.3/122°24.4
src
30.10
700.0
55
2.99
53
3953
30.9
24
«*
110
77
S15
8JAN86/152Q
47°37.7/122°24.6
SFC
28.42
1770.0
139
7.06
138
2847
100.3
78
65
321
293
S16
8JAN86/152B
47°38.2/122°24.7
src
28.17
1546.7
137
5.90
102
2421
103.7
62
19
390
120
S17
8JAN86/1541
47°38.1/122°25.1
src
2B.66
1370.0
102
5.36
98
2612

56
112
431
253
S18
8JAN86/1555
47°37.8/122°25.6
31c
28.89
1183.3
104
5.07
86
2729
70.9
47
107
2125
302
S19
8JAN86/1622
47°38.7/122°25.6
src
29.45
1393.3
114
6.85
126
2986
79.7
63
42
237
179
S20
8JAN86/1631
47°38.7/122°25.1
src
28.45
1858.0
125
7.07
127
2191
92.8
82
145
356
m
S21
9JAN86/0842
47°34.1/122°20.8
SEC
9.21
556.7
417
18.99
545
4786
574.7
241
420
15C9
1133
S22
9JAN86/0855
47°34.4/122°21.5
arc
14.85
3933.3
322
15.32
399
3709
391.4
200
223
1237
786
S23
9JAN86/0904
47°35.0/122°21.6
src
18.13
3660.0
262
13.01
339
3572
316.1
145
258
1012
788
S24
9JAN86/0914
47°35.5/122°21.6
sc
22.65
3106.7
216
10.45
232
2843
226.5
117
258
659
591
S25
9JAN86/0925
47°35.4/122°21.1
src
28.14
1320.0
104
6.81
141
3297
118.3
138
1524
2288
571
S26
9JAN86/0933
47°35.5/122°20.7
src
26.45
2135.0
169
8.73
133
2969
124.9
82
222
587
366
**Belcw Detection Level
-204-

-------
APPENDIX in. (Continued)	PARTICULATE CHEMISTRY DATA FOR ELLIOTT BAY
(in inits of wt./vol. of water)
L-RERP 86-1, Jarnary 8, 9, and 23, 1986


Position
Depth Sal
ISM
A1
XL
Q*
Ml
Fe
Ni
Qi
Zn
Pb
Statical Date/Time
N/W
m

V&L
VS/L
Ug/L
ng/L
ng/L
pg/L
ng/L ng/L
ng/L
ng/L
S27
9JAN86/0943
47°35.4/122°20.7
SEC
25.19
2186.7
171
8.95
178
2767
160.1
86
201
572
552
S28
9JAN86/0952
47*36.0/122°20.4
ScC
28.00
2030.0
175
9.31
162
2782
125.4
85
374
530
530
S29
9JAN86/1014
47°35.9/122°21.0
SFC
25.86
2890.0
158
7.31
146
3013
137.3
73
373
831
578
S30
9JAN86/1025
47°35.9/122°21.6
sc
27.20
1310.0
103
5.29
105
2876
89.7
54
166
356
252
S1
9HAN86/1035
47°35.6/122°22.3
sec
30.16
708.0
72
3.87
78
3236
43.3
42
59
183
152
S32
9JAN86/1043
47°35.4/122°22.1
SPC
25.64
1305.0
111
5.03
106
22T4
99.4
57
130
390
347
333
9JAN86/1051
47°£.1/122°22.1
SC
30.13
658.0
42
2.68
45
3367
28.6
22
15
429
94
S3"
9JAN86/1146
47°35.4/122°22.4
SC
30.01
672.0
61
2.76
63
2832
39.4
42
71
151
59
S35
9JAN86/1154
47°35.5/122°22.7
SEC
30.02
J66.0
34
1.57
32
2024
23.2
27
19
78
49
S36
9JAN86/1202
47°35.9/122°23.1
sec
30.16
766.7
46
2.12
33
2748
24.2
26
**
48
43
S37
9JAN86/1215
47°36.0/122°22.6
SEC
29.89
860.0
76
3.88
51
3275
43.2
42
41
197
89
S38
9JAN86/1235
47°36.1/122°21.5
sex:
27.68
1265.0
110
4.92
124
2696
88.0
60
43
3$
410
S39
9JAN8 6/1310
47°36.3/122°21.3
SEC
27" .68
1530.0
119
5.34
117
a547
95.1
57
89
422
295
S40
9JAN86/1319
47°36.4/122°20.8
SPC
27.39
1405.0
118
4.85
105
1926
84.3
51
52
2T0
215
S41
9JAN86/132T
47°36.3/122°20.4
SFC
27.44
2380.0
40
6.48
135
2592
106.4
77
146
461
282
S42
9JAN86/1333
47°36.4/122°20.5
SEC
27.83
1530.0
124
5.54
111
2101
100.7
54
99
355
165
S43
9JAN86/1340
47°36.3/122°21.0
SEC
27.89
1365.0
110
5.14
111
2276
86.0
67
54
321
174
544
9JAN86/1348
47°36.9/122°21.5
sec
27.06
1753.3
127
6.01
131
2404
107.9
72
16
352
109
S45
9JAN86/1400
47°36.7/122°21.9
sc
26.74
1295.0
125
5.42
132
2434
100.1
70
67
331
435
S46
9JAN86/1407
47°36.5/122°22.3
sec
27.48
1430.0
13
5.85
113
2514
100.2
67
86
414
452
S47
9JAN86/1421
47°36.3/122°22.9
sec
26.65
1190.0
140
6.70
105
2717
118.1
78
139
491
403
S49
23JAN86/1600
47°34.2/122°21.1
SFC
26.42
8613.3
827
39.67
693
8302
547.6
452
616
1698
1153
**BeIcw Detection Level
-205-

-------
'PENDIX IV.	PARTICULATE CHEMISTRY DATA FDR ELLIOTT BAY
(in uiits of wt./wt. of suspended matter)
L-RERP 86-1, Janiary 8, 9, and 23, 1986


Position
Depth Sal
TSM
A1
TL
Cr
Mi
Pe
Ni
Cu
Zn
Pb
tation Date/Time
N/W
m

Ug/L
%
%
ppm
ppm
%
ppm
ppm
ppm
ppm
I
8JAN86/0840
47°37.1/122°21.6
SEC
20.40
36000.0
2.34
0.21
40
336
2.4
23
184
403
282
?
8JAN86/0855
47°36.9/122°22.0
SFC
28.61
1876.7
7.32
0.38
81
1365
5.1
46
103
157
239
3
8JAN86/0924
47°36.6/122°22.4
SC
29.99
792.0
9.07
0.46
81
4743
5.0
41
38
191
157
3
8JAN86/0924
47°36.6/122°22.4
SC
29.99
792.0
8.35
0.42
77
4344
4.7
43
**
208
146
'4
8JAN86/0946
47°36.5/122°23.3
SPC
30.19
760.0
7.07
0.32
57
4774
3.5
39
**
157
58
5
8JAN86/1021
47°37.2/122°23.1
SFC
29.01
1290.0
8.56
0.42
83
2198
5.9
43
87
187
228
5
8JAN86/1021
47°37.2/122°23.1
SPC
29.01
1290.0
8.55
0.40
74
2122
5.7
44
94
191
197
5
8JAN86/1045
47°37.2/122°22.7
arc
29.22
1250.6
8.02
0.42
87
2471
5.7
42
129
216
196
5
8JAN86/1045
47°37.2/122°22.7
sc
29.22
1250.6
8.29
0.43
83
2507
5.7
37
158
213
201
7
8JAN86/1105
47°37.6/122°22.7
sec
27.36
1913.3
6.89
0.37
78
1430
5.5
40
177
303
312
3
8JAN86/1126
47°37.6/122°22.1
sc
27.92
3420.0
6.93
0.45
85
1209
5.4
61
**
104
101
3
8JAN86/1126
47°37.6/122°22.1
SFC
27.92
4016.7
5.45
0.41
71
961
4.6
49
44
106
84
9
8JAN86/1256
47°37.5/122°23.2
SFC
2T.79
2330.0
7.32
0.39
71
1345
5.5
41
98
251
249
10
8JAN86/1307
47°37.2/122°23.3
SFC
27.75
1403.3
7.51
0.40
77
1849
5.4
40
107
233
335
11
8JAN86/1320
47°36.9/122°23.5
SPC
29.94
796.0
7.16
0.40
59
4410
4.3
30
**
159
113
12
8JAN86/1331
47°36.7/122°23.3
SPC
30.04
704.0
7.57
0.36
76
4898
4.1
31
**
157
123
13
8JAN86/1400
47°36.8/122°23.7
SPC
30.00
658.0
6.28
0.38
57
4485
3.9
34
**
227
142
14
8JAN86/1411
47°38.3/122°24.4
sx:
30.10
700.0
7.79
0.43
75
5648
4.4
35
**
156
110
15
8JAN86/1520
47°37.7/122°24.6
sc
28.42
1770.0
7.86
0.40
78
1609
5.7
44
37
181
166
16
8JAN86/1528
47°38.2/122°24.7
3D
28.17
1190.0
8.78
0.56
88
2284
9.9
66
117
413
338
17
8JAN86/1541
47°38.1/122°25.1
SPC
£.66
1370.0
7.48
0.39
71
1907
0.0
41
82
315
192
18
8JAN86/1555
47°37.8/122°25.6
SFC
28.89
1183.3
8.78
0.43
73
2306
6.0
40
91
1796
255
19
8JAN86/1622
47°38.7/122°25.6
SPC
29.45
1393.3
8.21
0.49
90
2143
5.7
45
30
170
128
20
8JAN86/1631
47°38.7/122°25.1
SFC
28.45
1858.0
6.70
0.38
68
1505
5.0
44
78
192
150
21
9JAN86/0842
47°34.1/122°20.8
SEC
9.21
5386.7
7.74
0.35 101
888
10.7
45
78
SO
211
22
9JAN86/0855
47°34.4/122°21.5
SFC
14.85
3933.3
8.18
0.39 102
943
10.0
51
57
314
200
23
9JAN86/0904
47°35.0/122°21.6
SPC
18.13
3660.0
7.16
0.36
93
976
8.6
40
71
276
215
24
9JAN86/0914
47°35.5/122°21.6
SFC
22.65
3106.7
6.95
0.34
75
915
7.3
38
83
212
190
25
9JAN86/0925
47°35.4/122°21.1
SPC
23.14
1320.0
7.89
0.52 107
2498
9.0
105
1155
1733
432
26
9JAN86/0933
47°35.5/122°20.7
SPC
26.45
2135.0
7.90
0.41
62
1390
5.9
38
104
275
171
*Below Detection Level
-206-

-------
APPENDIX IV. (Continued)
PARTICULATE CHEMISTRY DATA FOR ELLIOTT BAY
(in uiits of wt./wt. of suspended matter)
L-RERP 86-1, Jaiuary 8, 9, and 23, 1986


Position
Depth Sal
"EM
A1
XL
Cr
Mi
Fe
Ni
Cu
Zn
Pb
Action Date/Time
Mt
m

yg/L
%
%
PF
ppn
%
ppm
ppm
ppm
ppm
S27
9JAN86/0943
47°35.4/122°20.7
SPC
25.19
2186.7
7.83
0.41
82
1266
7.3
39
92
261
252
S28
9JAN86/0952
47°36.0/122°20.4
sx:
28.00
2030.0
8.63
0.46
80
1370
6.2
42
184
261
261
S29
9JAN86/1014
47°35.9/122°21.0
SPC
25.86
2890.0
5.48
0.25
50
1042
4.8
25
129
as
200
S30
9JAN86/1026
U7°35.9/122°21.6
arc
27.20
1310.0
7.84
0.40
80
2196
6.9
41
126
272
200

9JAN86/1035
47°35.6/122°22.3
SPC
30.16
708.0
10.12
0.55
110
4571
6.1
59
83
259
215
S32
9JAN86/1043
47°35.4/122°22.1
SPC
25.64
1305.0
8.52
0.39
81
1743
7.6
44
99
299
266
S33
9JAN86/1051
47°35.1/122°22.1
SPC
30.13
658.0
6.38
0.41
68
5117
4.4
34
23
651
142
S3H
9JAN86/1146
47°35.V122°22.4
SFC
30.01
672.0
9.04
0.41
93
4214
5.9
62
105
225
88
S35
9JAN86/1154
47°35.5/122°22.7
SPC
30.02
486.0
6.92
0.32
65
4164
4.8
55
39
160
102
S36
9JAN86/1202
47035.9/122°23.1
SFC
30.16
766.7
6.05
0.28
42
3584
3.1
34
**
62
57
m
9JAN86/1215
47°36.0/122°22.6
3C
29.89
860.0
8.82
0.45
59
3808
5.0
48
47
223
104
S38
9JAN86/1235
47°36.1/122°21.5
SPC
27.68
1265.0
8.68
0.39
98
2131
7.0
47
34
265
324
S39
9JAN86/1310
47°36.3/122°21.3
SPC
27.68
1530.0
7.79
0.35
76
1730
6.2
37
58
276
193
S40
9JAN86/1319
47°36.4/122°20.8

27.39
1405.0
8.3T
0.35
75
1370
6.0
37
37
192
153
S41
9JAN86/1327
47°36.3/122°20.4
SFC
2T.44
2380.0
1.70
0.27
57
1089
4.5
32
61
194
118
S42
9JAN86/1333
47°36.4/122°20.5
SFC
27.83
1530.0
8.14
0.36
73
1373
6.6
35
65
232
108
#3
9JAN86/1340
47°36.3/122°21.0
SPC
27.89
1365.0
8.08
0.38
82
1667
6.3
49
40
235
127
S44
9JAN86/1348
47°36.9/122°21.5
SPC
27.06
1753.3
7.24
0.34
75
1371
6.2
41
9
201
62
S45
9JAN86/1400
47°36.7/122°21.9
sc
26.74
1295.0
9.65
0.42
102
1879
7.7
54
52
294
336
S46
9JAN86/1407
47°36.5/122°22.3
SPC
27.48
1430.0
9.01
0.41
79
1758
7.0
47
62
289
316
S47
9JAN86/1421
47°36.3/122°22.9
SPC
26.65
1546.7
11.55
0.38
66
1565
6.7
40
12
252
78
S49
23JAN86/1600
47°34.2/122°21.1
SPC
26.42
8613.3
9.61
0.46
80
964
6.4
52
72
197
134
**Below Detection Level
-207-

-------
APPENDIX V.	PARTICULATE CHEMISTRY DATA FDR COMMENCEMENT BAY
(in units of wt./vol. of water)
L-RERP 85-2, April 1-2, 1985

Position
Depth Sal
T34
A1
Ti
Cr
Mn
Fe
Ni
Cu
Zn
Pb
Statical Date/Time
N/W
a

Ug/L
yg/L
yg/L
ng/L ng/L
ug/L
ng/L
ng/L ng/L ng/L
C885-1 1AFR85/1145
47°16.57/122°25.02
5
29.53
712.7
44.9
2.16
41
1729
26.7
18
31
88
102


15
29.86
1000.0
84.3
3.89
53
3204
38.7
29
47
133
65
CB85-2 1APR85/1230
47°16.39/122°25.19
4
29.14
807.7
56.4
2.85
45
1990
32.6
19
41
108
139


40
30.15
1697.2
90.7
5.67
83
3156
56.4
41
57
143
109
C885-3 1AFR85/1243
47°16.29/122°25.43
4
29.zr
940.7
55.3
2.66
52
1709
29.4
25
42
155
202


40
30.18
1741.4 111.6
7.03
86
3496
67.2
45
31
160
124
CB85-4 1APR85/1342
47°l6.07/122°25.07
3
29.41
755.4
46.0
2.29
37
1563
25.8
19
58
97
77


10
29.69
703.6
45.3
2.30
45
1648
24.1
14
58
80
51


40
30.15
1681.3 114.0
7.21
89
3955
68.6
48
72
164
84
CB85-5 1APR85/1632
U7°17.35/122»26.15
4
30.27
2008.6
5.3
7.51
104
4319
72.8
58
70
178
80


100
30.27
2080.9
6.1
8.49
109
4674
79.5
62
69
225
114
CB85-6 1APR85/1917
47°17.05/122°26.a3
4
27.87
1313.9
72.9
3.97
79
1927
48.2
23
42
147
57


100
30.29
2074.1 112.3
7.14
92
3740
69.2
56
65
181
91
CB85-7 1APR85/2025
47°16.5/122°26.51
4
28.99
934.5
49.7
3.11
53
1723
33.0
20
23
109
41


20
29.90
646.9
42.6
2.55
35
2389
24.8
37
87
74
43


60
30.24
1270.0
81.4
4.97
73
4263
48.7
42
43
208
39


100
30.33
2336.1 138.0
9.39
118
4721
89.1
76
103
315
165
CB85-8 1APR85/2058
l«7017 -57/122?26.56
3
28.82
898.2
54.7
2.73
47
1737
34.6
28
35
152
62


90
30.29
1032.9
75.5
4.47
69
3767
43.6
45
26
133
38
CB85-9 1APR85/2133
47°17.32/122°26.57
3
28.60
902.0
49.3
2.51
32
1566
32.7
18
160
238
23


140
30.38
2020.4
95.6
8.52
110
4566
81.3
73
102
220
101
CB85-10 1AFR85/2216
47°16.58/122°Z7.47
3
29.59
575.6
31.4
1.94
32
1676
18.4
19
57
104
33


20
29.80
615.7
36.2
2.07
34
2314
21.1
18
19
69
28


75
29.92
602.9
37.4
2.31
36
2700
23.2
20
22
95
23


140
30.19
1814.9
92.0
759
98
4561
72.7
59
97
188
83
CB85-11 1APR85/2243
47°17.03/122°28.07
4
29.70
649.2
69.8
1.98
31
2071
20.4
17
25
72
16
<385-12 2AFR85/1018
47°18.32/122°20.48
4
29.23
717.4
80.4
2.09
31
1726
24.5
15
30
120
45


100
30.32
1878.6
295.4
7.43
99
4415
70.7
73
81
196
69
*Data Not Available
**Below Detection Limits
-208-

-------
APPENDIX V. (Continued)	PARTICULATE CHEMISTRY DATA FDR COMMENCEMENT BAY
(in uiits of wt./vol. of water)
L-RERP 85-2, April 1-2, 1985

Position
Depth Sal
131
A1
11
Cr
f-h
Fe
Ni
Cu
Zn
Pb
Station Date/Time
N/W
m

Ug/L
yg/L
ug/L
ng/L ng/L
ve/i-
ng/L
ng/L ng/L ng/L
CB85-13 2APR85/1134
&
•
OO
o
&
4
29.23
804.6
68.5
2.20
33
1650
24.4
13
14
82
53


20
29.93
379.6
41.5
1.11
18
1881
11.5
11
**
40
22


80
30.03
756.9
96.5
2.57
40
2950
25.6
23
20
81
30


160
30.45
1713.7
212.9
6.52
96
3429
63.6
63
89
237
103
CB85-14 2APR85/1329
47°18.36/122°30.36
4
29.65
2651.8
»
1.36
27
1679
15.0
14
51
55
40


85
30.43
211.4
*
7.07
94
3785
67.6
65
87
176
84
(385-15 2APH85/1522
47°19.05/122<,30.CW
3
29.37
534.8
51.2
1.52
36
1370
17.0
22
75
65
43


20
30.04
610.6
74.6
2.15
35
2606
21.4
21
16
64
38


60
30.29
940.9
126.4
3.78
58
3355
37.3
38
36
101
40


120
30.42
1673.4
210.0
6.87
92
3621
65.6
66
76
178
64
CB85-16 2APR85/1457
47®19.14/122
-------
APPENDIX VI.	PARTICULATE CHEMISIHT DATA FDR COMMENCEMENT BAY
(in uiits of wt./wt. of suspended matter)
L-RERP 85-2, April 1-2, 1985

Position
Deptii Sal
131
AL
11
Cr
Mh
Fe
NL
Cu
Zn
Pb
Station Date/Time
N/W
m

yg/L
%
%
PF
ppm
%
Ppm
ppm
ppm
ppm
CB85-1 1APR85/1145
U7°16.57/122°25.02
5
29.53
712.7
6.37
0.30
57
2U25
3.6
25
43
124
143


15
29.86
1000.0
8.56
0.39
53
3204
3.9
29
47
133
65
(385-2 1AFB85/1230
17°16-3S/122°25.19
4
29.14
807.7
7.09
0.35
56
2463
4.0
23
51
134
172


40
30.15
1697.2
5.35
0.33
49
1859
3.3
24
33
84
64
CB85-3 1APR85/1243
47°16.29/122°25.43
4
29.27
940.7
6.00
0.23
55
1816
3.1
27
45
165
215


40
30.18
1741.4
6.40
0.40
49
2007
3.6
26
47
92
71
CB85-4 1APR85/1342
47°16.07/122°26.07
3
3.41
755.4
6.20
0.30
50
2069
3.4
25
77
128
102


10
29.69
703.6
6.54
0.33
63
2342
3.4
20
83
114
73


40
30.15
1681.3
6.78
0.43
53
2352
4.1
28
43
98
50
CB85-5 1APR85/1632
47°17.35/122°26.15
4
30.27
2008.6
5.27
0.37
52
2150
3.6
29
35
89
40


100
30.27
2080.9
6.09
0.41
52
2246
3.8
30
33
108
55
CB8&-6 1APR85/1917
U7°17.05/122°26.25
4
27.87
1313.9
5.64
0.30
60
1466
3.7
17
32
112
43


100
30.29
2074.1
5.42
0.34
44
1803
3.3
27
31
87
44
CB85-7 1APR85/2025
47°16.35/122°26.51
4
28.99
934.5
6.40
0.33
56
1844
3.5
21
30
116
44


20
29.90
646.9
6.58
0.39
53
3693
3.8
57
134
114
66


60
30.24
12T0.0
6.41
0.39
57
3357
3.8
33
34
164
31


100
30.33
2336.1
5.91
0.40
50
2021
3.8
32
44
135
71
CB85-8 1AFH85/2058
47°17.57/122°26.56
3
28.82
898.2
6.16
0.30
52
1934
3.9
31
39
169
69


90
30.29
1033.0
7.31
0.43
66
3647
4.2
43
25
129
31
CB85-9 1APR85/2133
47°17.32/122°26.57
3
28.60
902.0
5.47
0.28
35
1736
3.6
20
178
254
25


140
30.38
2020.4
4.73
0.42
54
2260
4.03
36
50
109
50
CB85-10 1AFR85/2216
47°16.58/122°27.47
3
29.59
575.6
5.53
0.34
56
2913
3.2
34
100
181
57


20
29.80
615.7
5.94
0.34
55
3T59
3.4
S
30
112
46


75
29.92
602.9
6.27
0.38
59
4477
3.8
33
37
158
38


140
30.19
1814.9
5.07
0.42
54
2513
4.0
32
53
103
46
CB85-11 1APR85/2243
47°17.03/122°28.07
4
29.70
649.2
10.74
0.31
48
3191
3.2
26
38
110
25
CB85-12 2APR85/1018
47°18.32/122°20.48
4
29.23
717.4
11.21
0.29
43
2407
3.4
21
41
168
62


100
30.32
1878.6
15.72
0.40
53
2350
3.8
39
43
104
37
*Data Not Available
**BeIow Detection Limits
-210

-------
APPENDIX VI. (Continued)	PARTICULATE CHEMISTRY DATA FDR COMMENCEMENT Bffif
(in inits of wt./wt. of suspended matter)
L-RERP 85-2, April 1-2,1985

Position
Depth Sal
TSM
A1
TL
Cr
Mn
Fe
Ni
Cu
Zn
Pb
Station Date/Time
N/W
m

VS/L
%
%
ppm
ppm
%
ppm
ppm
ppm
ppm
CB85-13 2APR85/1134
47°18.38/122°£.38
4
29.23
804.6
8.51
0.27
41
2050
3.0
16
17
102
65


20
29.93
379.6
10.93
0.29
48
4955
3.0
28
**
106
57


80
30.03
756.9
12.76
0.34
52
3097
3.4
31
27
107
39


160
30.45
1713.7
12.42
0.38
56
2001
3.7
37
52
138
60
CB85-14 2APH85/1329
47°18.36/122°30.36
4
29.65
2651.8
*
0.05
10
633
0.6
5
19
21
15


85
30.43
211.4
*
3.34
444
17907
32.0
306
412
832
397
CB85-15 2APR85/1522
47019.05/122°30.04
3
s.ir
534.8
9.57
0.28
67
2562
3.2
40
140
122
80


20
30.04
610.6
12.22
0.35
57
4268
3.5
35
27
105
63


60
30.29
940.9
13.43
0.40
62
3566
4.0
40
38
107
43


120
30.42
1673-4
12.55
0.41
55
2164
3.9
39
46
107
38
CB85-16 2APR85/1457
47°19.1V122°S.43
3
3.37
625.0
9.25
0.27
45
2363
3.0
24
12
165
67


85
30.25
701.3
14.10
0.41
62
4698
4.1
38
42
121
39
*Data Not Available
**Below Detection Limits
-211-

-------
APPENDIX VII.
DISSOLVED TRACE METAL DATA FDR ELLIOTT BAY
L-RERP 85-2, APRIL 4-5, 1985


Position
Depth Sal

Cu
Ni
Cd
Zn
Pb
Fe Rem
Station
Date/Time
N/W
m
grt
-------
APPENDIX VIII. DISSOLVED TRACE METAL DATA FDR ELLIOTT BAY
	 L-RERP 86-11 JANUARY 8, 9 and 23, 1986


Position
Depth
Sal
Ml
Cu
Ni
Cd
Zn
Pb
Fe
Station
Date/Time
IVW
m
g/kg
yg/L
ng/L
ng/L
ng/L
ng/L
ng/L
ug/L
S1
08Jar£6/0840
47°37.1/122°21.6
0
20.40
14.20
5910
1030
247
33010
2570
6.15
S2
08Jan86/0855
47°36.9/122°22.0
0
26.61
7.81
410
330
72
2250
27
1.57
S3
08Jar66/0924
47°36.6/122°22.4
0
29.99
3.05
330
340
72
850
18
0.66
S4
08Jar£6/0946
47°36.5/122°23.3
0
30.19
2.34
320
390
68
640
20
0.41
S5
08Jar86/1021
47°37.2/122023.1
0
29.01
6.34
450
400
75
2000
36
1.28
S6
08Jarfi6/1045
47°37.2/122°22.7
0
29.22
5.17
390
390
69
1630
£
1.13
SI
08Jar66/1105
47°37.6/122°22.7
0
27.36
7.81
730
480
76
4040
50
1.90
S8
08JSmQ6/l 126
4703T.6/122°22.1
0
27.92
8.93
470
380
68
2400
19
2.69
S9
08Jarfi6/1256
47°37.5/122023.2
0
27.79
9.25
630
480
79
4130
74
1.82
S10
08Jarfl6/1307
47037.2/122023.3
0
27.75
6.39
520
360
72
2270
105
1.95
S11
08Jar86/1320
47036.9/122023.5
0
29.94
3.16
350
390
77
990
22
0.57
S12
08JanS6/1331
47°36.7/122°23.3
0
30.04
3.50
370
390
80
1180
36
2.84
S13
08Jarfl6/l400
47036.8/122023.7
0
30.00
2.88
350
370
79
880
19
0.44
S14
08Jarfi6/l4l1
4703B.3/122°24.4
0
30.10
2.90
360
370
77
990
20
0.63
S15
08Jarfl 6/1520
47037.7/122024.6
0
28.42
7.77
570
440
85
3240
44
1.44
S16
08Jiarfl6/1526
47038.2/122024.7
0
26.17
8.77
580
430
81
3220
41
1 .03
S17
08Jarfl6/1541
47038.1/122025.1
0
26.66
7.08
570
430
91
3080
72
1.45
S18
08JarfJ6/1555
47037.8/122025.6
0
28.89
6.63
490
390
86
2440
50
0.75
S19
08Jan86/l622
47038.7/122025.6
0
29.45
4.68
400
380
78
1770
20
0.84
S20
08Jam86/l631
47038.7/122025.1
0
28.45
7.40
430
320
72
2220
34
0.98
S21
09Jan66/0842
47°34.1/122°20.8
0
9.21
39.26
930
900
68
9210
39
18.17
S22
09J=ut86/0855
47°34.4/122°21.5
0
14.85
31.77
870
810
63
7780
20
9.00
S23
09Jarfi6/0904
47O35.0/122O21.6
0
18.13
25.70
830
710
75
7510
41
7.47
S24
09JiarB6/09l4
47035.5/122021 .6
0
22.65
14.31
520
430
55
3610
22
3.82
S25
09Jarfl6/0925
47035.4/122021.1
0
26.14
7.86
4960
670
155
20520
122
1.69
525
09JarB6/0933
47°35.5/122°20.7
0
26.45
12.98
570
530
93
3300
58
3.95
S27
09Jarfi 6/0943
47°35.4/122°20.7
0
25.19
20.12
770
690
98
5170
35
4.42
S28
09JanB6/0952
47O36.0/122O20.4
0
26.00
10.70
860
640
90
5150
73
2.24
S29
09Jar66/10l4
47°35.9/122°21.0
0
25.86
21.11
2140
860
122
8920
58
4.82
S30
09Jan86/1026
47035.9/122021.6
0
27.2D
9.79
610
540
85
4000
31
2.63
S31
09Jarfl 6/1035
47035.6/122022.3
0
30.16
3.31
380
380
80
120
34
0.59
S32
09Jarfl6/1043
47035.4/122022.1
0
25.64
6.88
1010
630
91
6090
54
4.11
S33
09Jarfi6/1051
47035.1/122°22.1
0
30.13
2.61
330
380
80
850
13
0.40
S34
09JanB6/1l46
47°35.4/122°22.4
0
30.01
3.96
480
510
86
1810
33
1.32
S35
09Jar66/1154
47°35.5/122°22.7
0
30.02
3.65
400
440
74
1880
30
0.87
S36
09Jan86/1202
47°35.9/122°23.1
0
30.16
3.03
350
400
83
1100
26
0.43
S37
09Jar86/1215
47°36.0/122°22.6
0
29.89
3.86
310
370
86
3210
24
0.63
S38
09Jan86/1235
47036.1/122°21.5
0
27.68
9.56
720
550
106
3330
42
2.36
S39
09Jan86/1310
47036.3/122021.3
0
27.68
9.33
630
510
85
5480
33
1.66
S40
09Jar66/1319
47036.4/122°20.8
0
27.39
10.07
590
490
84
4350
34
1.57
S41
09Jar66/1327
47O36.3/122O20.4
0
27.44
11.70
710
480
77
3690
160
9.32
S42
09Jar66/1333
47°36.4/122°20.5
0
27.83
8.76
530
480
78
3760
43
1.68
S43
09Jar86/1340
47o36.3/122°21.0
0
27.89
11.01
590
480
88
3740
96
4.22
S44
09Jari36/1348
47°36.9/122°21.5
0
27.06
It .33
610
640
94
4410
71
2.00
S45
09Jar66/l40Q
47036.7/122021.9
0
26.74
12.83
700
580
86
3460
45
2.06
S46
09Jan86/l407
47°36.5/122°22.3
0
27.48
11.06
710
530
97
3470
33
1 .64
S47
09Jar66/l421
47°36.3/122°22.9
0
25.65
13.55
780
520
83
5090
265
37.29
S49
23Jan86/l600
47034.2/122021.1
0
6.42
58.15
1160
760
69
6320
103
29.52
1) Contaminated by natural particulates.
-213-

-------
APPENDIX IX.
DISSOLVED TRACE METAL DATA FDR COMMENCEMENT BAY
L-RERP 85-2, APRIL 1-2, 1985

Position
Depth
Sal
Ml
Cu
Ni
Cd
Zn
Pb
Fe
Ran
Station
Date/Time N/W
m
S/kg
lig/L
ng/L
ng/L
ng/L ng/L
ng/L
vg/L

CB85-1
1Apr65/1138 47°16.9/121°24.9
1
29.58
2.11
495
454
92
112T
19
1.03

CB85-1

28
3.92
2.96
394
458
98
769
37
0.73

CB85-2
1Apr85/1210 47°16.7/121°25.5
1
22.65
6.25
573
412
75
1835
65
7.01

CB85-2

46
30.20
6.50
384
444
92
1140
68
20.14
1
CB85-2

46

5.39
370
431

1090
30

2
(385-3
1Apr85/1311 47°16.6/121°25.7
1
26.04
11.87
751
531
98
2642
80
7.64

CB85-3

58
30.08
7.66
437
464
91
1028
119
3.20
1
CB85-3

58

6.18
403
445

960
67

3
CB85-4
1Apr85/l431 47°16.1/121°26.2
1
29.35
2.76
507
451
92
1174
19
1.20

CB85-4

10
3.67
2.01
511
454
94
1255
36
1.13

CB85-4

55
29.97
2.55
419
555
111
1206
72
1.04

CB85-7
1Apr85/1957 47°16.7/122°26.8
1
29.51
2.74
763
444
93
1C99
16
0.67

CB85-7

20
29.97
2.99
476
418
89
826
12
0.46

CB85-7

60
3.95
3.31
382
421
91
548
45
0.53

CB85-7

117
30.32
9.22
345
432
89
663
2T
0.82

CB85-10
1Apr85/2154 47°17.2/122°2T.6
1
3.26
3.27
472
420
86
1054
17
0.83

CB85-10

20
3.94
2.51
466
396
87
847
20
0.47

(385-10

70
3.86
1.97
3T0
440
84
690
39
0.26

CB85-10

148
30.33
4.71
313
393
81
565
10
0.25

CB85-13
2Apr85/1056 47°18.7/122°20.7
1
3.27
2.99
439
406
83
1542
16
1.07

CB85-13

20
3.95
0.99
345
454
87
744
*
0.25

CB85-13

75
30.25
2.56
239
401
79
664
34
0.28

CB85-13

143
30.42
8.69
318
422
84
631
68
5.86
1
CB85-13

143

8.42
311
417

650
60

4
CB85-14
2Apr85/1311 47°18.6/122°29.7
1
29.62
1.91
385
404
83
785
15
0.52

C885-14

95
30.28
4.41
308
394
83
731
24
0.53

CB85-15
2Apr«5/1550 47°19.1/122°29.9
1
29.39
2.15
397
432
89
1552
19
1.09

CB85-15

20
3.93
0.87
312
28
80
782
6
0.23

CB85-15

60
30.27
2.74
269
396
81
726
9
0.25

CB85-15

155
30.42
459
255
386
80
673
*
0.29

*Below Detection Limit
1)	Field Logs indicated skewed filters. Contaminated by natural particulates
2)	Corrected assuming 35J of the particles passed into the dissolved sanple (see QA/QC text).
3)	Corrected assuming 42J of the particles passed into the dissolved sanple (see QA/QC text).
4)	Corrected assuming Q% of the particles passed into the dissolved sample (see QA/QC text).
-214-

-------
APPENDIX X. TRACE ORGANIC COMPOUNDS QUANTIFIED DURING THIS PROJECT
Phenanthrene (Phe)
Anthracene (Ant)
Methyl Phenanthrene (MPH)
(Four isomers)
Fluoranthene (FLa)
Pyrene (Pyr)
Retene (Ret)
Benzofluoranthene (BF1)
(Three-isomers)
Benzo(e)pyrene (BEP)
Benzo(a)pyrene (BAP)
Indeno Pyrene (IPY)
Benzo(g,h,i)perylene (BPe)
Chrysene (Chr)
Benz(a)anthracene(BAA)
DDE
DDD
DDT
Dichlorobiphenyls (CL2)
Trichlorobiphenyls (CL3)
Tetrachlorobiphenyls (CL4)
Pentachlorobiphenyls (CL5)
Hexachlorobiphenyls (CL6)
Heptachlorobipheyls (CL7)
Octachlorobiphenyls (CL8)
Nonachlorobiphenyls (CL9)
-215-

-------
APPEhDIX XI.
TRACE ORGANICS
(in total ng/g)
COLLECTED BY CENTRIFUGE 1/85
SAMPLE NAME
DATE/TIME
LATITIDE
LONGITUDE
LOCATION
VOL SAMPLED
S1SURF1
10185, 0930
17°35.1'N
122°21.6'W
ELLIOTT BAY
320L
S13JRF2
10185, 0930
17°35.1'N
122°21.6*W
ELLIOTT BAY
320L
S1-2Cta
H0385, 0800
17035.1*N
122021.6'W
ELLIOTT BAY
715L
S2SURF
40885, 0900
17°36.3'N
122°21.2'W
ELLIOTT BAY
615L
S3SUHF
10985, 0930
17°36.8'N
122022.8'W
ELLIOTT BAY
621L
SlSURF
10385, 2130
17°37.2'N
122°21.6«W
ELLIOTT BAY
633L
S1-2CH1
10185, 2230
17°37.2'N
122°2l.6,W
ELLIOTT BAY
621L
S6SUHF
10185, 1830
17°17.0'N
122°27.0'W
COW. BAY
638L
S6-20m
10285, 0800
17°17.0*N
122°27.0'W
COM. BAY
618L
Phe
67
130
1100
120
380
310
110
780
350
Ant
21
26
210
160
110
120
100
95
160
MPh
57
110
1200
t
730
150
t
1200
560
Fla
120
120
3500
1100
1100
790
580
920
110
Pyr
110
310
2900
1100
1100
790
580
720
150
Ret
68
210
1900
910
900
t
920
520
130
BAA
12
92
870
170
110
260
310
200
120
Chr
69
150
1100
110
610
390
320
350
190
BF1
110
230
2300
760
1100
710
710
510
380
BEP
52
86
1100
260
230
260
250
220
110
BAP
15
75
780
210
260
190
180
150
110
iPy
37
71
710
170
210
160
170
150
110
BPe
37
81
760
170
210
170
180
210
110
DDE
<0.35
<0.17
<2.9
<0.69
<1.1
<1.1
<2.9
<0.17
<1.0
DDT
<1.1
<0.70
<11
<2.7
<5.7
<1.6
<12
<1.9
<1.0
DDD
<1.1
<0.70
<11
<2.7
<5.7
<1.6
<12
<1.9
<1.0
CL2
<0.35
<0.17
<2.9
<0.69
<1.1
<1.1
<2.9
<0.17
<1.0
CL3
<0.35
1.33
<2.9
<0.69
10
<1.1
9.1
<0.17
<1.0
CLl
0.6
<0.28
<1.6
r.i
11
<1.1
<1.7
<0.75
<1.6
CL5
2.5
1.5
250*
5.5
<2.3
2.1
13
15
65
CL6
3.2
3.1
31
9.1
13
1.1
<2.9
6.5
1.5
CL7
<0.7
2.0
9
1.6
1
<1.8
<1.7
1.7
3-9
CUB
<0.55
<0.28
<1.6
<1.1
<2.3
<1.8
<1.7
<0.75
<1.6
CL9
<1.1
<0.56
<9.1
<2.2
<1.6
<3.7
<9.1
<1.5
<3.2
*
t
one large peak fits the criteria outlined in the QA/QC document but upon firtlner investigation uas shown by a 1 ion GCMS scan rot to be a
PCB. This peak acoounts for 210 ng/g of this aigf.
qiantitation vaa precluded by an inteak.

-------
APPENDIX XII.
TRACE ORGANICS
(in total ng/g)
COLLECTED BY SEDIMENT TRAPS
MOORING#
DEPTH (m)
START/STOP
LATITUDE
LCNallUDE
LXATICN
85-1/17
6m
32985 , 6235
47°37.0'N
122°22.7'W
ELLIOTT BAY
85-1/20
50m
32985 , 62285
47°37.0'N
122°22.7'W
ELLIOTT BAY
85-2/18
95m
32985 , 6225
47°37.0'N
122°22.7'W
ELLIOTT BAY
85-4/15
6m
32685, 41585
47°17.6'N
122°27.5'W
CCM4. BAY
85-5/16
15Qn
32585, 41585
47°17.6'N
122°27.3'W
CCM4 BAY
Phe
590
820
440
<260
190
Ant
160
2T0
190
<260
53
MPh
320
670
360
<260
370
fla
1000
930
720
<260
240
Pyr
900
850
630
<260
200
Ret
150
330
260
<260
400
BAA
340
330
260
<260
62
Or
710
580
410
<260
90
BF1
520
580
560
<260
124
BEP
320
330
250
<260
84
BAP
210
230
280
<260
90
IPy
210
230
230
<260
90
BPe
210
230
280
<260
90
IDE
12
<5.2
<.18
<26
<.15
DDT
<21
<21
<.71
<104
<.61
DCD
<21
<21
<.71
<104
<.61
CL2
<5.2
<5.2
<.18
<26
<.15
CL3
<5.2
<5.2
<.18
<26
<•15
CL4
<8.3
<8.4
5.5
<42
0.7
CL5
12
<8.4
15
<42
2.2
CL6
33
<5.2
12
<26
2.3
CL7
<8.3
<8.4
5.9
<42
1.4
CL8
<8.3
<8.4
3.2
<42
<.24
CL9
<17
<17
.81
<84
<.48
-217-

-------
APPENDIX XIII.
TRACE ORGANICS
(in total ng/g)
COLLECTED BY CENTRIFUGE 1/86
SAMPLE NAME
DATE/TIME
LATITUDE
LONGITUDE
LOCATION
VOL SAMPLED
S1SURF1
10886, 1250
47°37.1 *N
122°21".6'W
ELLIOTT BAY
140L
S1SURF2
10886, 1250
47*37.1*N
122°2t,6'W
ELLIOTT BAY
193L
S2SURF
10986, 0950
47°35.0'N
122°21.5'W
ELLIOTT BAY
510L
S3SURF
11085, 0915
47°36.6'N
122°2T.3'W
ELLIOTT BAY
525L
Phe
15000
14000
1100
950
Ant
3000
2700
380
420
MPh
24000
22000
1300
960
Fla
12000
13000
3600
2100
Pyr
9400
9000
3400
1800
Ret
<320
<310
230
260
BAA
2100
1900
950
730
Chr
2900
2500
1600
1100
BF1
3100
2000
3100
2200
BEP
1400
1200
1400
720
BAP
1800
1300
1200
790
IPy
1400
1100
1200
670
BPe
1400
1100
1100
620
DDE
<8.8
<12
<2.1
<1 .6
DDT
<35
<50
<8.5
<6.5
DDD
<35
<50
<2.1
<6.5
CL2
<8.5
<12
<2.1
<1.6
CL3
<8.5
32
<2.1
<1 .6
CLM

-------
APPENDIX XIV.
STORM DRAIN CALCULATIONS
Area drained by seven major storm drains discharging to west waterway = 1569
acres (Tetra Tech 1986)
1569 acres x 43,560 ftl/acre = 68,345,640 ft1
Rainfall for January 8-9, 1986 - 0.0375 ft (NOAA NWS 1986)
68,345,640 ft2 x 0.0375 ft = 2,562,962 ft3 = 72.75 million L rainfall
collected.
Duwamish River flow 32 mVsec (2 days) (86,400 sec/day) - 5,529,600 m3/2 days
Low PAH Loading of Storm Drain Effluent
0.4 mg PHA/L (Tetra Tech 1986)
(72.75 * 106L) (0.4 mg/L) - 29.1 kg PAH
Assume PAH put into waterway at constant rate:
29.1 kg PAH / 2 days
29.1 kg PAH / 5,529,600 m3 river water in 2 days = 5.3 mg/m3
At Spokane Street tine waterway depth is 9m but the fresh water depth is
5m at 32 m3/sec flow rate (Santos and Stoner, 1972)
(5.3 mg/m3) (9/5) =9.5 mg/m3
(9.5 mg/m3y [l0~l{3/cm3) =9.5 ng/L
High PAH Loading of Storm Drain Effluent
2.2 mg PAH/L (Tetra Tech 1986)
(72.75 x 10®L) (2.2 mg/L) = 160.1 kg PAH
Assume PAH put into waterway at constant rate:
160.1 kg PAH / 2 days
160.1 kg PAH / 5,529,600 m3 river water in 2 days =» 29 mg/m3
At Spokane Street the waterway depth is 9m but the fresh water depth is
5m at 32 m3/sec flow rate (Santos and Stoner, 1972)
(29 mg/m3) (9/5) - 52 mg/m3
(52 mg/m3) (106m3cm3) = 52 ng/L
-219-

-------
APPENDIX XV.
TRACE METALS IN SEDIMENT TRAP SAMPLES
(in units of wt./wt. sample)
Mooring
Bay
Depth
Vertical mass
Cu
Mn
Cd
Pb


ppm
flux (g/m"lday"1)
ppm
ppm
ppm

85-1
Elliott
6
0.09 (0.16±0.07)
52
553
*
100


52
0.11 (0.16±0.05)
76
1113
3.60
229
85-2
Elliott
95
7.3 <7.7±1.9)
61
1725
0.17
76
85-4
Commencement
6
0.22 (0.22±0.07)
52
625
0.16
68
85-5
Commencement
150
31.7 (29.3±8.7)
57
1436
0.21
48
*Below Detection Limit
-220-

-------
APPENDIX XVI.
Elliott Bay Plume Mapping Data
Station
Depth
Date/Time
Position
Cor. Sal.
Temp
Atten
SPM

(m)

N/W
(ppt)
(C)
(1/m)
(mg/L)
EB85-SBDRO
0.00
4Apr85/09l8
47°35.01/122°21 .54
9.5
3.60
8.00
10.64

0.50


10.5
4.00
7.10


1.00


18.2
7.80
4.50


2.00


20.2
7.90
3-70


3.00


25.7
8.00
1 .60


0.00


12.4
7.80
7.10

EB85-SBT1
0.00
4Apr85/0608
47°35.41/122°22.52
22.1
9.90
1.20
1 .06

1.00


27.9
8.40
0.70


0.50


27.1
8.40
1 .00


0.25


27.0
8.30
1.00

EB85-SB3
0.00
4Apr85/1019
47°35.42/122°21.53
10.0
8.20
7.80
8.56

0.25


12.9
8.00
8.00


0.50


11.9
8.00
7.80


1.00


25.0
8.10
1.60


2.00


27.9
8.10
1 .00

SB85-SBT2
0.00
4Apr85/1025
47"35.53/122°20.90
18.7
8.70
2.90


0.50


22.6
8.70
2.40


1.00


23.6
8.20
2.60

SB85-SBT3
0.00
4Apr85/1031
47°35.62/122°20.62
14.4
8.20
6.50


0.25


14.4
8.10
4.70


0.50


20.0
8.00
3.50


1.00


20.7
8.00
3.20


1 .50


23.6
8.20
1 .60

EB85-SB1
0.00
4Apr85/1038
47°35.96/122°20.43
21.6
8.40
2.70
3.31

0.50


22.1
8.20
2.60


1.00


23.1
8.20
2.10


1 .50


23.9
8.20
1 .90


0.00


21.1
8.50
2.80

EB85-SB4
0.00
4Apr85/1047
47°35.90/122°21.63
16.1
8.30
4.80
7.53

0.25


17.8
8.30
4.60


0.50


22.3
8.20
2.50


1.00


24.5
8.20
1.70


2.00


26.7
8.10
1 .20

EB85-SBT4
0.00
4Apr85/1217
47°35.77/122"22.70
19.1
8.60
1.00


0.25


19.3
8.50
1.10


0.50


23.1
8.60
1.20


1 .00


26.5
8.60
1 .10


1.50


27.1
8.40
1.00

EB85-SB8
0.00
4Apr85/1224
47°35.97/122°23.20
27.7
8.50
1 .00
1 .01

0.25


26.0
8.40
1.00


0.50


26.0
8.40
0.90


1.00


27.2
8.30
0.70


1 .50


28.8
8.30
0.70

EB85-SBT5
0.00
4Apr85/1229
47*36.13/122"23.28
27.4
8.50
1.00


0.25


27.6
8.50
1 .00


0.50


27.8
8.40
0.90


1 .00


28.1
8.40
0.80


1.50


28.6
8.30
0.70

-221-

-------
APPENDIX XVI. (Continued) Elliott Bay Plume Mapping Data
Station
Depth
Date/Time
Position
Cop. Sal.
Temp
At ten
SPM

(m)

N/W
(ppt)
(C)
(1/m)
(mg/L)
EB85-SB5
0.00
4Apr85/1238
47°36.30/122°21 .67
19.2
8.70
3.70
4.86

0.25


20.4
8.70
3.10


0.50


22.4
8.50
2.30


1.00


26.2
8.40
1.20


1 .50


27.2
8.20
1.30

EB85-SB2
0.00
4Apr85/1246
47°36.31/122°20.71
18.7
8.40
4.30
3.50

0.25


19.0
8.30
3.50


0.50


18.8
8.30
3.40


1 .00


21.4
8.30
2.50


1.50


26.0
8.30
1.50


2.00


26.5
8.20
1 .30

EB85-SB6
0.00
4Apr85/1257
47°36.72/122°21.06
17.9
8.80
4.00
4.22

0.25


18.5
8.70
3.70


0.50


20.0
8.50
3.20


1.00


21 .8
8.20
2.40


1.50


24.8
8.30
1.70


2.00


26.2
8.30
1 .20

EB85-SBT6
0.00
4Apr85/1311
H7°36.55/122°22.57
24.1
8.70
2.20


0.25


23.9
8.40
1 .90


0.50


25.9
8.40
1.40


1 .00


26.8
8.30
1 .20


1.50


27.3
8.30
1.20


2.00


27.4
8.30
1 .10

EB85-SB9
0.00
4Apr85/13l6
47°36.70/122*22.95
26.2
8.40
1.50


0.25


26.0
8.50
1 .70


0.50


26.2
8.50
1.50


1 .00


26.5
8.50
1 .40


1.50


27.0
8.30
1.30


2.00


27.1
8.30
1.30

EB85-SBT7
0.00
4Apr85/1327
47o36.52/122°24.03
28.2
8.50
0.80


0.25


28.5
8.50
0.80


0.50


28.6
8.60
0.80


1 .00


28.6
8.60
0.80


1.50


28.7
8.40
0.80

EB85-SB13
0.00
4Apr85/1343
47°36.80/122°24.66
28.9
8.50
0.70
0.41

0.25


28.9
8.40
0.70


0.50


28.9
8.40
0.70


1.00


28.9
8.40
0.70


1 .50


28.9
8.40
0.70

EB85-SBT8
0.00
4Apr85/1333
47°36.79/122°2H.58
24.5
8.70
1.80
2.16

0.25


26.5
8.60
1 .10


0.50


28.1
8.50
0.80


1.00


28.7
8.50
0.80


1.50


28.8
8.50
0.80


0.00


25.2
8.80
1 .80

EB85-SBT9
0.00
4Apr85/1349
47°37«12/122°24.67
23.6
8.70
2.10
2.43

0.25


24.7
8.60
1 .90


0.50


26.0
8.50
1.50


1 .00


27.1
8.50
1.10


1.50


27.9
8.40
0.80


2.00


28.1
8.40
0.80

-222-

-------
APPENDIX XVI. (Continued) Elliott Bay Plume Mapping Data
Station
Depth
Date/Time
Position
Cor. Sal.
Temp
At ten
SPM

(m)

N/W
(ppt)
(C)
(1/m)
(mg/L)
EB85-SBT10
0.00
4Apr85/l400
47°37.22/122°22.60
20.4
9.00
2.90


0.25


20.4
9.00
2.90


0.50


20.4
9.00
2.90


1.00


25.5
8.50
2.80


1 .50


27.0
8.40
1.20


2.00


28.3
8.30
1.10

EB85-SB7
0.00
4Apr85/l408
47<,37.26/122°22.22
21 .0
8.60
3.40
3.94

0.25


21.1
8.70
3.60


0.50


20.2
8.90
3.50


1.00


23.1
8.50
2.30


1 .50


24.1
8.30
1 .80


2.00


26.0
8.20
1.50

EB85-SBT11
0.00
4Apr85/l4l8
47°37.53/122°22.07
21.1
8.80
2.50


0.25


21.0
8.70
2.50


0.50


21 .0
8.70
2.50


1.00


21.6
8.50
2.50


1 .50


23.1
8.30
1 .80


2.00


27.0
8.30
1.10

EB85-SB10
0.00
4Apr85/l425
147037.40/122 °23.22
20.2
8.90
2.90


0.25


20.4
8.90
2.90


0.50


22.1
8.70
2.70


1.00


24.5
8.70
1.60


1.50


26.5
8.30
1.40


2.00


26.7
8.30
1.30

EB85-SBT12
0.00
4Apr85/H33
47°37.40/122°23.40
21.3
8.80
2.80


0.25


21.5
8.80
2.80


0.50


22.1
8.70
2.60


1.00


25.2
8.60
1.80


1 .50


26.5
8.40
1.30


2.00


28.4
8.40
0.90

EB85-SB1H
0.00
4Apr85/l439
47038.17/122"24.88
21 .6
8.90
2.50
2.66

0.25


21.6
8.90
2.50


0.50


21 .6
8.90
2.50


1 .00


21.8
8.90
2.40


1 .50


22.6
8.60
1 .80


2.00


27.7
8.60
1.00

EB85-SBT13
0.00
4Apr85/l449
48°38.19/122°25.51
25.9
8.80
1 .40
1 .44

0.25


25.9
8.80
1.40


0.50


26.0
8.80
1.40


1 .00


28.1
8.60
0.90


1 .50


28.6
8.50
0.80


2.00


28.8
8.40
0.80

EB85-SBT14
0.00
4Apr85/1501
47°38.56/122°25.60
21 .8
8.90
2.20
3.44

0.25


22.3
8.90
2.20


0.50


22.3
8.80
2.00


0.75


26.0
8.60
1.10


1 .00


27.1
8.40
0.80


1.50


28.9
8.30
0.70


2.00


29.0
0.00
0.00


0.00


22.4
8.80
2.20

-223-

-------
Appendix XVII.
QUALITY ASSURANCE PROJECT REPORT
FOR FIELD INVESTIGATIONS TO SUPPORT
ELLIOTT BAY AND COMMENCEMENT BAY CONTAMINANT TRANSPORT STUDY
Prepared by
Paci£ic Marine Environmental Laboratory
Prepared for
U.S. Environmental Protection Agency, Region X
Seattle, Washington
March, 1985
Approvals:
PMEL Project Manager
PMEL
Project Coordinator
-224-

-------
Section No. 	2	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 1 of 	1
CONTENTS
1.
Title and Signature Page
2.
Table o£ Contents
3.
Project Organization and Responsibilities
4.
Objectives for Measurement
5.
Sampling Procedures
6.
Sample Custody
7.
Calibration Procedures and Frequency
8.
Analytical Procedures
9.
Data Reduction, Validation, and Reporting
10.
Internal Quality Control Checks
11.
Performance and System Audits
12.
Preventative Maintenance
13.
Corrective Actions
14.
References
15.
Appendix A - Compounds Measured
-225-

-------
Section No. 	3	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 1 of 1	
PROJECT ORGANIZAITON AND RESPONSIBLITIES
Project organization and individuals responsible for quality assurance
are as follows:
Project Manger:	Herbert C. Curl, Jr.
Project Coordinator:	Richard A. Feely
QA Officer - organics:	Paulette P. Murphy
QA Officer - trace metals	(AA): Anthony J. Paulson
QA Officer - trace metals	(XRF): Terri L. Geiselman
EPA Project Officer:	John Underwood
EPA Region X QA Officer:	Barry Town
-226-

-------
Section No. 	4	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 1 of 	7
OBJECTIVES FOR MEASUREMENT
Quality assurance objectives for precision, accuracy, and completeness
have been established for each measurement parameters, and are presented in
Table 1.
CTD, transmissivity, total suspended matter and current meter measurements
The Plessey CTD is calibrated in accordance with procedures
NOIC-CP-04A. Data coverted through calibrations are field checked to provide
salinity to ±0.01 and pressure to ±1.0 decibars. The accuracy of the
Montedoro Whitney salinometer-temperature probe is ±0.5 ppt for salinity and
±0.5°C for temperature. The Plessy bench salinometers provide salinity
measurements to 0.003 ppt for discrete samples. Sensors carried by moored
instruments, current speed, directions, temperature, conductively and
pressure, have the accuracies of ±1 cm sec-1 or ±2%, whichever is greater, ±5
degrees, ±0.15 degrees C, 0.1% of range, and ±1% of range respectively. The
accuracy and precision of the Cahn balances are ±0.0012% and ±0.001 mg,
respectively. The precision of total suspended matter measurements is
nominally 0.01%. The shipboard sampling precision for total suspended matter
is highly dependent on location, depth and elapsed time. Sampling precisions
for total suspended matter reported for the main basin of Puget Sound have
ranged between 1.0% and 17%. The accuracy and linearity of the beam
transmissometer is ±0.5% and 0.1%, respectively. Light attenuation time
series over nine hours taken in Puget Sound have been reported by Baker (1984)
and are too complex to summarize as a single precision value.
-227-

-------
Section No. 	4	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 2 of 	7
Organic analysis:
Accuracy is affected by matrices and recovery. Recovery standards are
spiked into all samples at the Soxhlet extraction stage. Reported
concentrations are adjusted with these recoveries. Recoveries are typically
greater than 80%. The precision of our method is determined by replicate
runs. The coefficient of variance is routinely within 20%. The
sampling/analytical variability is determined by duplicate samples. Samples
were simultaneously collected at Sta. 1 surface (4/85) using two
centrifuges. Two samples were collected at Sta. 5 surface over a two day
period (4/85). One sample (Sta. 1, 1/86) was split into two fractions and
analyzed separately. The results of these precision checks are included in
the data tables. The limit of quantitation for aliphatic and aromatic
hydrocarbons analyzed in our laboratory is 0.25 ng. An expression of this
number in concentration units is dependent upon the sample matrix, volume in
the final extract, amount of extractable material available, and integrity of
the blanks. For our laboratory the limit of quantitation ranges from 1 ppb to
50 ppb (ng/g) for sample sizes of 0.1 to 30 g dry weight. The limit of
quantitation is determined for each sample by multiplying 0.25 ng by the
volume of solvent in the vial and dividing by the dry weight of sediment
extracted. The limit of quantitation for chlorinated hydrocarbons is between
0.025 and 0.10 ng/uL depending on the isomer. This corresponds to 17 to
5000 pptr (pg/g) for sample sizes of 0.1 to 30 g dry weight.
-228-

-------
Section No. 	4	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 3 of 7	
Suspended particulate trace metal analysis:
Total elemental compositions (Mg, Al, Si, P, S, CI, K, Ca, Ti, Fe, Cr,
Mn, Ni, Cu, Zn, Pb, and As) in suspended particulate matter are determined by
X-ray primary- and secondary-emission spectrometry using the thin-film
technique (Baker and Piper, 1976; Feely et al., 1981; Holmes, 1981). A Kevex
Model 7077-0700 x-ray energy spectrometer with a rhodium x-ray tube is used in
the direct and secondary-emission (Ge and Zr targets) modes to obtain maximum
efficiency for excitation of individual elements in the sample. Thin-film
standards are prepared from suspensions of finely ground U.S. Geological
Survey Standard Rocks (W-l, AGV-1, GSP-1, G-2, BCR-1, BHVO-1, MAG-1, GXR-1,
GXR-3, and GXR-5; 90 percent by volume less than 15 ym in diameter), NBS
Standard Reference Materials (SRMs) (#1571, Orchard Leaves; #1577, Bovine
Liver; #1648, Urban Particulates; and #1645, River Sediment), National
Research Council of Canada Standard Reference Materials (MESS-1 and BCSS-1),
and National Institute of Environmental Studies of Japan Standard Reference
Materials (Pond Sediment and Pepperbush Powder). Calibration is effected
using standard regression techniques. Standards are analyzed before and after
grinding by atomic absorption spectrophotometry.
The sources of the reference values for the thin-film standards used in
accuracy tests are: USGS Rock Standard W-l for Mg, Al, Si, K, Ca, Ti, Cr, Mn,
Fe, Ni, Cu, and Zn; NBS SRM 1571 (orchard leaves) (Flanagan, 1976) for P and
S; USGS-AEG Rock Standard GXR-1 (Abbey, 1980) for As; and NBS SRM 1645 (river
sediment) for Pb.
For Mg, Al, Si, K, Ca, Ti, Cr, Mn, Fe, Ni, Cu, and Zn the measured value
was obtained from a standard that was prepared by passing a suspension of the
-229-

-------
Section No. 	4	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 4 of 	7
finely ground rock through a 37 urn nylon mesh followed by collection of the
suspensate (353 urn) on a Nuclepore filter identical to those used for sample
acquisition. Replicate XRF analyses of this standard were then randomly
chosen from 53 sequential days of analyses during which this filter served as
a stability monitor. Single analyses of the respective standard filters for
P, S, CI, As and Pb were performed*
The precision is given in terms of the units of measurement (Wt.% and
ppm) and as a coefficient of variation (C.V. = error #	por
mean value
particulate Mg, Al, Si, K, Ca, Ti, Cr, Mn, Fe, Ni, Cu, and Zn the mean and la
error values were determined from 10 replicate measurements, each of which was
obtained on a different analysis day. For particulate P, S, As, and Pb and
dissolved S, CI, K, Ca, Mn, and Fe the precision data represents the standard
estimate of error (Sy.x = /£2i	a"n-2	ai	where aQ an,j 3l are the
calibration regression line intercept and slope, respectively) resultant from
calibration regressions.
The determination limits are based on counting statistics and are defined
as:
Determination Limit = 3 * Minimum Detection Limit
1 /TB
= 3 (2 • K • -=-£)
~T p
Where K = standard concentration in desired units (WT% or ppm),
T = counting or analysis time in seconds,
Ig = background intensity in counts-per-second, and
I = net peak intensity in counts-per-second.
-230-

-------
Section No. 	4	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 5 of 	7
Sediment trap particulate trace metal analysis!
The intra-laboratory quality control is based on measurements of
procedural blanks and analytical precisions. The procedural blanks suggest
that the analyses of sediment trap particulates are not jeopardized by
laboratory contamination. Analytical precisions have been found to be less
than 10% using the method described in the Analytical Procedures section.
The measurement of accuracy relies heavily on the analysis of standards
from outside the laboratory. The standards MESS-1 and BCSS-1 (National
Research Council of Canada) and MAG-1 (U.S. Geological Survey) were used to
determine accuracy.
Dissolved trace metals analysis;
The intra-laboratory quality control is based on measurements of
procedural blanks, extraction efficiencies and analytical precisions. The
field filtering blanks suggest that the analyses of these metals are not
jeopardized by field or laboratory contamination. Extraction efficiencies
have been determined by spiking a low concentration seawater sample with a
known amount of trace metal and extracting the spiked sample. The results of
a extraction efficiency experiment performed in 1984 show that the extraction
efficiency for all metals wa3 greater than 90%. The analytical imprecision
was generally less than 10% (Paulson, 1986).
Quality control procedures also utilize the the expertise of
investigators outside this laboratory. The open ocean standard NASS-l was
analyzed and all elements except Fe were within the range of the reported
-231-

-------
Section Ho. 	4	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 6 of 	7
values. The newly released nearshore CASS-1 standard will be analyzed as part
o£ this project.
Variations in the extraction efficiency, natural variability and random
contamination by sampling, filtration or analytical procedures can combine to
limit our ability to define the concentration of a trace metal at a particular
depth at an exact station location. In 1930, ten samples from 100 m were
collected during four casts at a single station using four different Go-Flo®
bottles in order to determine the overall precision of our measurements. The
sampling and processing precisions for dissolved Mn, Cu, Ni and Cd were 4%,
3%, 82 and 1% respectively.
The detection limit for the dissolved trace metal sampling, filtration
and analysis are controlled by either the instrumental or procedural blank.
The detection limits range from 0.001-0.060 yg/l for a 1-L sample filtered in
the field.
-232-

-------
Section No. 	4	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 7 of 7	
Table 1
Precision, Accuracy and Completeness Objectives
Measurement
Parameter
(Method)
Medium
Precision
Std. Deviation
Accuracy
Completeness
PAH
(GC-FID)
PCB's/DDT
(GCMS)
Trace Metals
(AA)
Trace Metals
(XRF)
Trace Metals
(AA)
suspended	± 20%
particulates
suspended	± 20%
particulates
sediment	± 10%
trap
particulates
suspended	± 10%
particulates
seawater	± 20%
90-110%
90-110%
85-100%
90%
90%
90%
90%
90%
(a) samples corrected with recovery standards - see text.
-233-

-------
Section No. 	5	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 1 of 6	
SAMPLING PROCEDURES
Sampling procedures for CTD-transmissivity and current meter measurements
In 1985, deep water CTD-Transmissometer measurements were made with a
Plessy system attached to a rosette sampler. At each station, a vertical
profile is obtained on the downcast while discrete samples are taken on the
upcast. The transmissometer windows are cleaned with particle-free water and
the output signal is measured prior to each cast. A calibration bottle with
reversing thermometers is tripped at the bottom of each cast. Discrete
samples are drawn from the Go-Flo® sampling bottles and the salinity is
measured by Plessy 6230N and 6345 bench salinometers. In 1985, shallow
measurements were also made from a small boat employing a battery-operated
salinometer CTM-1 (Montedoro-Whitney) with an attached transmissometer (Sea
Tech). Discrete samples were also collected with 1-L linear poLyethylene
bottles. In 1986, the Plessy CTD was used exclusively with similar
procedures.
Moored sediment traps, transmissometers and current meters (Baker and
Milburn, 1983) were located throughout the water column at three stations in
Elliott Bay and two stations in Commencement Bay during the spring of 1985.
The complete list of sediment traps, current meters and transmissometers
which were deployed is listed in Table 2. Upon recovering the
transmissometers, the quality of the output is verified and a calibration is
performed. During the deployment and recovery of the moorings, field CTD
profiles are taken as a quality control measure.
-234-

-------
Section No. 	5	
Revision No. 3 (November 1986)
Date November 01, 1986	



Page 2
of 6

Table 2.
Location and Duration of
Moored Equipment


Mooring
Location
Instrument
Depth
Duration

PS85-01
47"37'02"N 122°22'42"W
CM/T
1
3/27-7/9



CM/T
4
3/27-4/22



S3T
6
3/29-6/22
(204)


S3T
50
3/29-6/22
(204)


CM
52
3/27-7/9

PS85-02
47°37'06"N 122°22'42"W
S3T
95
3/29-6/22
(204)


CM/T
98
3/27-7/9



CM/T
101
3/22-7/9

PS85-03
47*35'00"N 122°21,34,,W
CM/T
2
3/28-6/12



S3T
3
3/29-5/23
(120)


CM/T
10
3/28-6/12

PS85-04
47917,44"N 122*27'31"W
CM/T
13
3/25-4/15



CM/T
4
3/25-4/15



S3T
6
3/26-4/15
(48)
PS85-05
47°17'39"N 122*27'15"W
S3T
150
3/26-4/15
(48)


CM/T
152
3/25-4/15

S3T - Sequentially Sampling Sediment Trap (hours per cylinder cycle).
CM - Current Meter
CM/T - Current Meter with Transmissometer
-235-

-------
Section No. 	5	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 3 of 	6
Sampling procedures for organic analysis of particulates:
All subsampling instruments are rinsed with CH2Cl2 (lot-tested highest
purity commercially available) immediately prior to use. The collection jars
are prepared in advance by the following procedure: they are washed in soapy
water, rinsed thrice with tap water and once with distilled water, then oven-
dried. This is followed by two successive CH2Cl2 rinses. The jars are
covered immediately with aluminum foil (twice-rinsed with CH2C12) and a screw
cap. Sediment traps are soap and water washed and acid rinsed. Sediment trap
blanks are monitored by extracting the brine/azide solution from an extra
sample tube. All centrifuge parts and tubing in contact with samples are
washed and solvent rinsed as above.
The centrifuge samples are transported from the ship-board freezer to the
laboratory freezer in the custody of the chief field chemist (maximum time one
hour). Sediment trap samples are refrigerated on board the ship and
transported to the laboratory in the same fashion as for sediment samples.
The bound field sampling book, contains the following information: exact ship
location, time of sampling, a listing of all subsamples taken, remarks on
unusual events and observations, and names of field scientists. This book is
cross-referenced to the laboratory analysis book. Sample labels include the
following information: sample location, subsample number, date, and field
sampling book reference.
Storage of centrifuge samples on the ship (up to one week) is at -10°C
and at -40°C in the laboratory for up to twelve months prior to analysis.
Sediment trap samples are maintained at 4°C on the ship (up to one week) and
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Section No. 	5	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 4 of 	6
at 4°C in the laboratory. These samples are subsampled within two weeks of
recovery and then frozen at -40°C.
Sampling procedures for trace metals in suspended and sediment trap particulates:
Total suspended matter samples are collected in acid-cleaned twelve liter
Go-Flo® sampling bottles (General Oceanics) using a rosette sampler. Samples
from small boat operations are collected in acid-cleaned 1-L linear
polyethylene (LPE) bottles. One to two liters of water are filtered under
vacuum through pre-tared acid cleaned filters (0.4 ym, 37 mm Nuclepore). The
filters are removed from the Teflon holders in a clean environment van or
portable laminar flow bench and are stored in individual plastic, acid cleaned
petridishes. The filters are desiccated over sodium hydroxide for about 48
hours. Reference filters from the same filter lot are stored and desiccated
along with the samples to evaluate changes in weight by the filters due to
humidity. All records concerning collection, filtration and storage are
recorded on the Suspended Particulate Field Log.
Sediment trap samples are obtained from moored arrays which have been
deployed in Puget Sound for three-month periods. A rotating chamber design
permits individual samples to be collected for six days after which a new
chamber is positioned under the opening. The lucite collection cylinders are
cleaned before deployment for twenty-four hours in 6N HC1 and then rinsed with
deionized water (Milli-Q®). The sample cylinders are filled with a brine
solution of about 40 ppt which contains sodium azide to prevent biological
oxidation from producing anoxic conditions in the cylinders. Upon recovering
the sediment traps, the material was collected on filters as described above.
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Section Ho. 	5	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 5 of 	6
After the traps are recovered, individual cylinders are mixed by
inversion and three 30 ml aliquots of the slurry are removed. The samples are
sieved on an acid cleaned Nylon screen (64 pm) and the material passing
through the screen is then filtered (0.4 yra, 47 mm Nuclepore). The samples
are dried at room temperature over NaOH. If the filter contains more than
2 mg, the dried sediment is removed from the filter and stored in acid cleaned
polyethylene vials. The material is then ground with a boron carbide mortar
and pestle.
Sampling procedure for dissolved trace metals:
Dissolved trace metal samples are collected in modified 12-L Go-Flo®
sampling bottles attached to a Keviar line. Standard Go-Flo® bottles are
modified by replacing all 0-rings with silicone O-rings and replacing the
spigot with a Teflon stopcock. The ends of the bottles are covered with new
clean plastic bags whenever they are not on the Keviar line. Samples from the
small boat operations are collected with 1-L LPE bottles.
Prior to each cruise, all-Teflon Savillex filtering apparatus and 50 mm
0.2 pm Nuclepore filters are acid-cleaned, assembled and rinsed by processing
1 L of 0.1 N nitric acid through each apparatus. Quartz-distilled water is
then processed through each apparatus. During the field sampling, the Go-Flo
sampling bottle is connected to the filtering apparatus by attaching a Teflon
tube into the stopcock. Five hundred mL are then filtered through the system
and discarded. The subsequent aliquots are transferred to a LPE bottle. To
collect any metals which may have absorbed to the walls of the apparatus
during filtration, 1 mL of concentrated Ultrex® HN03 per liter of sample is
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Section No. 	5	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 6 of 	6
added to the last aliquot before transferring the sample to the bottle. Each
bottle has been cleaned in hot hydrochloric acid and soaked in nitric acid for
a week. The bottles containing the sample are bagged, transported to the
laboratory at the end of the cruise and refrigerated until analysis. All
operations in which the sample is exposed to the atmosphere are performed in a
class 100 laminar flow hood. If the filtering apparatus is reused, a new
acid-cleaned filter is placed in the apparatus and the apparatus is then
recleaned by rinsing with 1 L of 0.1 N HN03. All records for collection,
filtration, preservation and storage are recorded on the Dissolved Trace Metal
Field Log.
Sampling frequency
The following samples were collected as part of this project:
April 85 April 85 January 86 Complete-
Commencement Elliott	Elliott	ness
Bay	Bay	Bay
Sediment trap
Organic particulates
Trace metals-Particulates
Trace metals Dissolved
2
2
40
27
3
6
74
30
3
48
100%
100%
100%
48
96%
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Section No. 	6	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 1 of 	2
SAMPLE CUSTODY
Sample custody is a vital aspect of remedial investigation programs
generating data that may be used as evidence in a court of law. Sample
custody at PMEL is documented using EPA chain-of-custody protocols whenever
samples leave the custody of the PMEL QA officer. Normally the QA officers at
PMEL collect, analyze, and compile the data for all samples.
During the April 1985 cruise, all samples from the McArthur were
processed on board and transported to the laboratory for analysis by the QA
Officers. Samples for dissolved and particulate trace metals were also
collected by small boat by the Project Coordinator. Upon returning to the
McArthur, the QA Officers for trace metals checked the bottle numbers against
the field sampling logs and found no discrepancies.
During the 1986 cruise, the Organic QA Officer collected and transported
samples to the laboratory for processing and analysis. The samples for
dissolved and particulate trace metals were collected by the Project
Coordinator or QA Officer, sealed and transported to the laboratory by the QA
Officer or personnel under his supervision. The QA Officers checked the
bottle numbers against the field sampling Logs, found no discrepancies and
proceeded to process the samples in the laboratory.
In 1986, the control of the sediment particulate samples were turned over
to Marilyn Roberts for analysis by GFAAS. No chain-of-custody documents were
processed.
The QA officers are responsible for verifying the data entered on field
and laboratory records. Records are kept in bound notebooks. The following
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Section No.	6	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 2 of 	2
procedures were documented in section 6 and 8:
*	reagents and supplies
*	preservatives
*	documentation of sample collection and tracking
*	transportation of samples.
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Section No. 	7	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 1 of 	3
CALIBRATION PROCEDURES AND FREQUENCY
Calibration procedures, calibration frequency, and standards for
measurement parameters and systems are shown in Table 2.
The primary organic standards are prepared by commerically available
reagents of < 97% purity in either hexane or CH2C12. The primary standards
are stored at -20°C and are tested annually. Standards were cross-checked
with R. Barrick, University of Washington.
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Section No. 	7	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 2 of 3	
Parameter/System
Plessy CTD
Montedoro-Whi tney
Plessy Salinometer
Balances
Organics/
Gas Chromatograph
Dissolved Trace
Metals/Graphite
AA
Sediment Trap
Particulates/Graphite
AA
Trace Metals in
Particulates/XRF
Current meter
Transmissometer
Table 3
Calibration procedures and frequency
Calibration (a)
each station (b)
Prior to cruise
daily
each day
daily (c)
calibrate daily
recalibrate .daily
calibrate daily
recalibrate daily
calibrated annually
monitored daily
annually
during cruise
(each cast)
Standard
I.A.P.S.O.
I.A.P.S.O.
I•A.P.S.O.
NBS Traceable
Intercalibration
with U of W
NBS Traceable
NBS Traceable
USGS or NRC
NW Regional
Calibration
Center
filtered
seawater
(a)	Instruments are calibrated by running quantitative standards to determine
response factors or linear response curves. Calibrations are recorded in the
instrument log books. (See Section 10.)
(b)	The CTDs are calibrated periodically by the Northwest Regional Calibration
Center and monitored against discrete bottom samples taken at each station.
Both the reversing thermometers and the salinometers used to make discrete
bottom measurements are calibrated by the Northwest Regional Calibration
Center.
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Section No. 	7	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 3 of 	3
(c) Calibration standard mixtures are prepared from primary standards. The
mixture is checked by GC analysis to verify actual amounts of each standard at
the time it is prepared and before each major project. It is stored at
-20°C. For convenience, a small aliquot is taken at the beginning of each
week and stored in the refrigerator for the week's daily GC calibration runs.
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Section No. 	8	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 1 of 	6
ANALYTICAL PROCEDURES
Organic analysis;
All reagents are of the highest purity available. Methanol is the only
solvent we use which consistently does not meet our standard of purity as it
comes from the manufacturer. We routinely distill it in our laboratory and
check each batch. Me have recently been able to obtain GC2 grade methanol
from Burdick and Jackson, thus eliminating our need to redistill methanol.
Each lot of all our solvents is also checked in the following manner: The
volume of solvent used in the procedure is concentrated and exchanged into
hexane. Blanks are acceptable if there are no interfering peaks.
Suspended matter is collected in 200 ml tubes containing sodium azide in
high salinity seawater. Reagent grade sodium aside and sodium chloride are
added ta filtered 3eawater to yield 22 SaNj concentration with salinity of
40 ppt. Following sample collection and trap recovery, the samples are
divided into three parts* Each sample tube is shaken, then approximately one
third of the resuspended sample is measured out. The combined sample (one
third from each of ten tubes) is poured through a size No. 60 sieve and the
<250 pm portion frozen at -40°C until analysis.
Sediment samples are homogenized by thorough stirring. Approximately
30 grams are transferred to a pre-extracted cellulose thimble in a pre-
extracted soxhlet extractor unit. A volume of 100 ml CH30H is cycled through
for 24 hours, followed by 100 ml of 65% CH2Cl2/35% CH3OH mixture for 48
hours. The extracts are combined and partitioned with 100 ml twice-distilled
water. The water fraction is rinsed twice with 20 ml aliquots of CH2C1j. The
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Section No. 	8	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 2 of 6	
combined sample and two rinses are re-partitioned with a fresh 100 ml portion
of re-distilled water. The water is again rinsed twice with 20 ml of CH2C12.
The combined sample and rinses are concentrated to approximately 40 ml
which is put through a cleanup column of 10 grams lot-tested 100/200 mesh
activated silica gel. The sample is eluted by AO ml CH2C12» This sample is
concentrated to 1 ml and exchanged into 2 ml of hexane.
Silica/alumina gel chromatography is carried out as follows: The column
is prepared with 5 g of 80/200 mesh lot-tested activated alumina followed by
10 g of lot-tested 100/200 mesh activated silica gel, and topped with one
centimeter of activated copper. The 2 ml sample is pLaced into the column and
rinsed with 20 ml pentane followed by 65 ml 50% pentane/50% CH2C12, then
25 ml CH2C12. Three fractions are collected; two, the aliphatic and PAH
fractions are analyzed in our laboratories.
The PAH fraction is concentrated to 1 ml and further fractionated on a
pre-calibrated Sephadex LH-20 column using a solvent mixture of 6 parts
cyclohexane/4 parts CH3OH/3 parts CH2C12.
All fractions to be analyzed are concentrated to 1 ml and exchanged into
hexane in preparation for GC injection. The volume in the vial is reduced
under N2. Final volume of the extract is typically 20-100 ul.
Hydrocarbon analysis is performed on a Hewlett Packard 5880 GC using
fused silica capillary columns with a flame ionization detector. The injector
temperature is 300°C, the detector 350°C. The oven temperature program is as
follows:
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Section No. 	8	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 3 of 6	
50° for 1 minute
30°/minute to 100'C
3°/minute to 280°C
280°C maintained for 30 minutes
All injections are manual, in the splitless mode, with injection port
backflush 30 seconds after the run begins.
Analysis for chlorinated compounds is done on a Hewlett Packard 5880 CG
using a DB5 fused silica column with a 5970B mass selective detector in single
ion monitoring mode. The 62 minute run is divided into 8 time segments. For
each segment 6 ions are monitored. These are the most abundant and second
most abundant ions for 3 different compound groups. By judicious choice of
the time window and ions selected, most PCB isomers plus DDT, DDD, and DDE can
be monitored. The injector temperature is 300°C and the oven temperature
program is as follows:
50° for 1 minute
30°/minute to 100°
3°/minute to end of run 62 at minutes
GC/MS analyses to confirm the identity of compounds in the PAH fraction
are carried out in a full scan mode on a Hewlett Packard 5970B mass selective
detector interfaced with a 5880 GC using fused silica capillary columns (J & W
Scientific DB5 30 m long, 0.25 mm ID, and .25 um film thickness).
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Section No. 	8	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 4 of 6	
Particulate trace metal analysis
Total elemental compositions (Mg, Al, Si, P, S, CI, K, Ca, Ti, Fe, Cr,
Mn, Ni, Cu, Zn, Pb, and As) in suspended particulate matter are determined by
X-ray primary- and secondary-emission spectrometry using the thin-film
technique (Baker and Piper, 1976; Feely et al., 1981; Holmes, 1981). A Kevex
Model 7077-0700 X-ray energy spectrometer with a rhodium X-ray tube is used in
the direct and secondary-emission (Ge and Zr targets) modes to obtain maximum
efficiency for excitation of individual elements in the sample. Thin-film
standards are prepared from suspensions of finely ground U.S. Geological
Survey Standard Rocks (W-l, AGV-1, GSP-1, G-2, BCR-1, BHVO-1, MAG-1, GXR-1,
XR-3, and GXR-5; 90 percent by volume less than 15 um in diameter), NBS
Standard Reference Materials (SRMs) (#1571, Orchard Leaves; #1577, Bovine
Liver; #1648, Urban Particulates; and #1645, River Sediment), National
Research Council of Canada Standard Reference Materials (MESS-1 and BCSS-1),
and National Institute of Environmental Studies of Japan Standard Reference
Materials (Pond Sediment and Pepperbush Powder). Calibration is effected
using standard regression techniques.
Sediment trap particulate trace metal analysis:
The sediment trap particulates are dissolved using the method of Eggimann
and Betzer (1976) and analyzed by graphite furnace atomic absorption
spectrometry (GFAAS) using a Perkin-Elmer Zeeman 5000 spectrometer equipped
with a HGA-500 graphite furnace and an AS-40 automatic sampler using standard
conditions (Perkin-Elmer, 1977) with slight modifications when necessary. The
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Section No. 	8	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 5 of 6	
dissolution of the sediment trap particulates is accomplished by placing 2 mg
of sediment trap particulates into a teflon digestion bomb (Bombco, Inc.),
adding 0.75 mL of concentrated Ultrex® HC1, placing the bomb in boiling water
for 30 mins., cooling the bomb, adding 0.25 mL of Ultrex® HN03, placing the
bomb in boiling water for 30 min., cooling the bomb, adding 0.05 mL of
Ultrex® HF and pLacing the bomb in boiling water for 90 min. After cooling,
the solution is transferred to an acid cleaned 1-oz LPE bottle. The bomb is
rinsed three times with quartz-distilled water (Q-H2O) into the 1-oz LPE
bottle and the weight of the eluate is increased to 20 gm with Q-Hz0.
Procedural blanks are obtained by performing the dissolution step in an empty
bomb. In the event that less than 2 mg is recovered from a single trap
cylinder, the particulates are left on the filter and the filter itself is
placed into the bomb. The procedural blank for this operation consists of
performing the dissolution step on a reference filter from the same lot as
that used for the sediment trap particulates.
Dissolved trace metal analysis:
The trace metal analyses are performed by graphite furnace atomic
absorption spectrometry (GFAAS) using a Perkin-Elmer Zeeman 500 spectrometer
equipped with a HGA-500 graphite furnace and an AS-40 automatic sampler using
standard conditions (Perkin-Elmer, 1977) with slight modifications when
necessary. A modification of the Chelex-100®, ion-exchange, pre-concentration
procedure following the method of Kingston et al. (1978) is used as described
in Paulson (1986). All apparatus are made of polyethylene or Teflon and are
acid-cleaned. Reagents are made by diluting Ultrex® acid (HN03), base (NH^OH)
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Section No. 	8	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 6 of 	6
or salt mixtures (NHhOH and acetic acid) with Q-H20 to the appropriate
molarity.
Ion-exchange columns are prepared by soaking 5.0 g of 200-400 mesh
Chelex-100® in 2.5 M HN03 for two hours, and then decanting and soaking in
clean 2.5 M HNO3 for another two hours. This slurry mixture is poured into a
fritted polyethylene Isolab column, allowed to drain, washed with 30 mL of
2.5 M HN03, rinsed with 30 mL of Q-H20, and converted to the ammonium form by
eluting with 10 mL of 2 M NH|,0H. Excess NH^OH is removed by rinsing with
30 mL of Q-H20. The prepared columns are placed in a plexiglass rack and the
effluent end of the column is attached to a peristaltic pump (Manostat) with
silicon tubing. The weighed samples (500 to 1000 g) are neutralized to pH 2
with concentrated NH^OH, buffered with 10 mL of 1 M NH^Ac, adjusted to pH 5.4
with concentrated NH|,0H and transferred to 1000-ml Teflon separatory funnels
(Nalgene). Five mL of the sample is placed in the prepared column and an air-
tight seal is formed between the column and the funnel by placing the tip of
the separatory funnel through a hole in a #5 hollow stopper (Nalgene) and
firmly inserting the stopper into the top of the column. The stopcock is
opened and the flow rate of the pump is adjusted to 0.15 mL/minute. When no
solution remains above the column, the column is rinsed with 10 mL of Q-H20,
rinsed with 30 mL of 10M NH^Ac in order to remove excess sea salts and eluted
with 20 mL of 2 M HN03 into a pre-weighed 30-mL (LPE) bottle. The eluate is
analyzed by GFAAS using calibration against standards prepared in a similar
HNO3 matrix.
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Section No.	9	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 1 of 8	
DATA REDUCTION, VALIDATION, AND REPORTING
CTD, transmissivity, total suspended matter and current meter measurements
Digitally recorded data from CTD and moored sampling instruments are
coverted to engineering units by applying the calibration relations determined
by the North West Regional Calibration Center. Current speed data are
converted using factor supplied relations. The salinity is calculated based
on the depth, temperature and conductivity. A temperature and salinity offset
is applied to the field CTD data based on the differences between the discrete
measurements of salinity and temperature and those calculated from the CTD
calibrations. The accuracy of the moored temperature and salinity data is
evaluated based upon field measurements during the deployment and recovery of
the mooring. Converted data are reported at 1 decibar intervals for CTD
data, and at the sample interval for moored instruments.
Transmissometer DC output is converted to a frequency output for
compatability with the CTD acquisition system. Attenuation is calculated by:
a = -In (T/100)
R
where a = attenuation (— )
m
R = light path length (m)
T/100 (% transmission) = -,000514f + 8.229
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Section No. 	9	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 2 of 	8
The percent transmission - frequency (f) relationship is a least squares
regression in which the coefficients are derived from frequencies with the
light path open in air and with the path blocked.
The relationship between attenuation and SPM is determined by regressing
attenuation with SPM concentrations. This relationship is reassessed as
SPM/water mass characteristics change.
For the 1985 study, the surface (<2 m) relationship was:
SPM = 1.35 a -0.45
r2 = .91 (Fig. 1)
Salinities measured with the Montedoro-Whitney salinometer were corrected
by regressing calibration surface samples against representative salinometer
measurements. The equation for best fit was calculated as:
salinity (ppt) = (.97 ^calibration salinity) + .810
r2 = .97
Organic analysis:
PAH compound identification and quantitation by GC with FID detector is
performed by comparison with the standard mixture which is injected at least
once daily. The data processing system selects and integrates those peaks
with retention times near the retention times of the standard mixture
compounds.
A manual check of chromatograms is also performed to check that the
correct peak has been integrated and that there are no peak shoulders or other
anomalies. Compound identity is confirmed by GCMS. Amounts for each compound
are calculated as follows:
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Section No. 	9		
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 3 of 8	
Fig. 1. Attentuation vs. suspended particulate matter in Elliott Bay for
L-RERP 85-2.
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Section No
9
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 4 of 8	
AMT(A) =
(Area). RF. AMTt„
A A IS
(Area)IS RFjg
Amt A
ng of compound A in the total extract.
where: RF^
response factor of compound A determined from the daily
calibration runs.
ng of the internal standard added prior to GC analysis.
response factor of the internal standard determined
from the daily calibration runs.
Following extraction the particulate matter in the soxhlet thimble is dried at
100°C overnight, cooled and weighed. This dry weight is used in the
calculation of ng/g for compound A. The quantifiable limits for all PAH
compounds is 0.25ng/yl and all process blanks are below that limit.
Chlorinated compound identification by GC/MS is based on retention time
and fragment abundance ratios. Standards were run to determine retention time
limits and characteristic ion fragment patterns for each compound for which
the pure isomer was available. For sample analysis two characteristic ion
fragments were selectively monitored for each group of compounds, for example,
ions 360 and 362 for hexachloro PCB's. Selection of a peak, for quantitation
is based on 1) retention time agreement for the primary and secondary ion
peaks to within 0.015 minutes 2) area for the secondary ion peak within 20% of
the expected value. Detection limits and linearity were established by
analyzing a series of standard mixture dilutions. Ion fragment peak areas <70
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Section No. 	9	
Revision Mo, 3 (November 1986)
Date November 01, 1986	
Page 5 of 8	
were disregarded and the foLlowing quantitation thresholds in ng/yl were
established:



DDE
0.025
CL5
0.040
DDD
0.10
CL6
0.025
DDT
0.10
CL7
0.040
CL2
0.025
CL8
0.040
CL3
0.025
CL9
0.080
CL4
0.040


The amount of each compound in the sample is determined by the equation shown
on the previous page. AIL process blanks are below the quantitation
thresholds.
Trace metal analysis of suspended particulates by XRF:
The reported values for trace metals in suspended particulates will be
calculated in the following manner:
C if a
cone (sample) = WT
where: cone (sample) is concentration of sample in ppm,
C is net countsKsec cm2),
We is weight of particulates on filter in mg,
A is effective area of filter and,
S is slope of net counts/sec cm2 vs. ng/cm2
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Section No. 	9		
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 6 of 8	
Trace metal analysis of sediment trap particulates by GFAAS:
The reported value for trace metals in sediment trap particulates will be
calculated in the following manner:
„ , , \ _ cone (eluate) * Wt (eluate)
Cone (sample)	Ht		
where:	Cone (sample) is the concentration of the sample in ppm (parts
per million)
Wt (eluate) is the weight of eluate in gms;
Wt (sample) is the weight of sample in mg and
Cone (eluate) is weight of the eluate in yg/Kg and is
determined
by the following:
Cone (eluate) » ABS	(BUnk)
where:	ABS (eluate) is the absorbance of the eluate, ABS (Blank) is
the
absorbance of the procedural blank and S is the slope of a
linear calibration curve of absorbance vs concentration of
standards.
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Section No. 	9	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 7 of 8	
Trace metal analysis of seawater by GFAASt
The reported value for dissolved concentration will be calculated in the
following manner:
/ , i /Cone (eluate) * Wt (eluate) - FFB ^
Cone (sample) - (	Ht (aampU)	> " »
where: cone (sample) is the concentration of sample in vg/L,
Wt (eluate) is the weight of acid eluate in gra,
Wt (sample) is the weight of sample extracted, in gm
FFB is the field filtering blank in ng,
p is the density in Kg/L and'
Cone (eluate) is the concentration of the eluate in
Vg/Kg, and is calculated by:
Cone (eluate) - ABS	(l.B.)
d
where:	ABS (eLuate) and ABS (l.B.) are the absorbance of the eluate
and
instrumental blank, respectively and
S is the slope of a linear calibration curve of the absorbance
vs. concentration of standards.
In the case of outliers, the sample will be disqualified if abnormal
procedures are noted in the collection or analytical logs. If no
abnormalities are noted, the sample will be reported with a qualifier based an
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Section No. 	9	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 8 of 	8
the relationship of enrichments between elements. For instance, if there are
large enrichments for Fe and Pb but smaller enrichments for Cu, Zn, and Ni,
contamination by natural particulates is probably the cause for the
enrichments.
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Section No. 	10	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 1 of 5	
INTERNAL QUALITY CONTROL CHECK
Organic chemistry:
9 Replicate samples are collected in the field for each type of sample
(i.e. centrifuge particulates, and sediment trap particulate).
0 Selected samples are split and run every 12-30 samples to assess
analytical precision.
° Blanks spiked with all quantified compounds are run every 6 samples.
0 A procedural blank is run every 1-7 samples beginning with Soxhlet
extraction of an empty thimble.
9 ^Recovery standards are added to each sample.
9 All reagents and dispensers are checked monthly.
9 Calibration standards are checked annually.
Trace Metals in Particulates:
Sensitivity for trace metals in particulates is monitored daily with USGS
or NRC standards. Six filters from each lot of 100 will be used for blank
purposes.
Trace Metals in Sediment Trap Particulates:
The analysis of trace metals in sediment traps by GFASS was limited by
the instrumental detection limit and not by procedural blanks. The triplicate
analyses of solid standard reference material is listed in Table 4. The
analtyical precision for a Puget Sound sample ranged between 1% and 19%.
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Section Mo. 	10	
Revision No. 3 (November 1986)
Date November 01, 1986
Page 2 of 	5
Dissolved Trace Metals:
Reagents used for extraction of a batch of 20 samples are pre-tested for
contamination. The variability in the reagent blanks did not determine the
detection limits. Four field filtering blanks were processed during the April
1985	cruise and three field filtering blanks were processed during the January
1986	cruise. The results of these analyses are presented in Table 5 along
with the instrumental detection limit. For Mn, Cu, Ni, Cd and Pb, the
detection limit was determined by the instrumental detection limit while the
detection limit for Zn and Fe was determined by the variation in the field
filtering blank. Four aliquots of the seawater standard CASS-1 (National
Research Council Canada) were analyzed as part of the QA/QC program of this
study. The analysis of Cu, Ni, Cd, Pb, Mn and Zn were within the range of
tolerance while the analysis of Fe indicated an extraction efficiency of 86%
(Table 3). The Fe results were not corrected for the low efficiency. The
analytical precision ranged between 3% and 11%.
Analysis of four samples [CB85-2(46m), CB85-3(58m), CB85-13(143m) and
EB85-5(95m)] indicated concentrations of dissolved Fe higher than those in the
surrounding locations. Examination of the field logs indicated that the
filter used in the first three high Fe analyses was skewed and thus the
dissolved sample was probably contaminated by natural particulates. An
attempt was made to correct for this contamination by natural particulates by
assuming an actual dissolved Fe concentration similar to that found at other
stations in the area (0.85 ug/L), calculating the percentage of particulates
in these dissolved samples based on the particulate Fe concentration which was
collected from a separate filtration process, and then correcting the results
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Section No.	10	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 3 of 	5
of the other metals using this percentage of particulates in the dissolved
sample and the total particulate trace metal concentrations (in units
ofng/L). Both the actual and corrected values are given in the results
table. The EB85-5(95m) sample was not corrected because there was no
indication in the field logs of the filter being skewed. However, this sample
was noted as possibly being contaminated by natural particulates.
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Section No. 	10	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 4 of 5	
Table 4. Quality Control Data for Trace Metals in Sediment Trap Particulates
Standard
Cu	Mn
ppm	ppra
Cd
ppm
Pb
ppm
BCSS	Mean	18±1 227±13 0.35+.07 24±2 7
Established 18+3 229+15 0.25+.04 23±3
MAG
Mean	28±1 651+15 0.33±.06 29±3 2
Established 27	650	N/A	24
MESS
Mean	32+5 472+78 0.60±.01 32±1 2
Established 25±4 513+25 0.59±.l 34±6
Sample Prec.
(X CV)
19
MDL
12
0.15
MDL = Minimum Detection Limit
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Section So. 	10	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 5 of 5	
Table 5. Dissolved Trace Metal Quality Control Data for L-RERP 85-2 and 86-1.
Parameter
Mn
Cu
Ni
Cd
Zn
Pb
Fe
Rem

ug/L
ng/L
ng/L
ng/L
ng/L
ng/L
ug/L

Instrumental DL
0.7
230
700
30.0
230
170
0.140
1
L-RERP 85-2








Processing BL
<0.03
<10
<30
<1
76
<6
0.130
2
+/- 1 std




6

0.026

Reported DL
0.03
10
30
1
18
6
0.078
3
Based On-
IDL
IDL
IDL
IDL
PB
IDL
PB

L-RERP 86-1








Processing BL
<0.03
<10
<30
1.9
42
<6
0.048
2
+/- 1 std



0.2
6

0.52

Reported DL
0.03
10
30
1
18
6
0.156
3
Based On-
IDL
IDL
IDL
IDL
PB
IDL
PB

Cass-1 Std.








Observed
2.44
268
303
30.0
10
225
0.750
n=4
+/- 1 Std
0.18
23
9
1.0
30
20
0.080

Reported	2.27 291 290 26.0 980 251 0.870
+ /- TL	0.17 27 31 5.0 99	27 0.080
DL = Detection Limit
TL = Tolerance Limit (Berman, pers. comm.)
BL = Blank
1)	Based on three limits the standard deviation of a blank graphite tube.
Includes loss of sensivity due to dilutions and use of matrix modifiers.
2)	Based on a 500 gm sample and a 20 gm eluate giving a concentration factor
of 25.
3)	Based on the Instrument Blank and concentration factor (IDL) or three time
the standard deviation of the Processing Blank (PB).
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Section No. 	11	
Revision Wo. 3 (November 1986)
Date November 01, 1986	
Page 1 of 	1
PERFORMANCE AND SYSTEMS AUDITS
Analyses are normally performed in-house by the QA officers. In cases
where the analyses are not performed by the QA officer, the QA officer will
audit the results based on the internal quality control data. The procedures
in Section 10 ensure adequate quality control. The laboratory participates in
NOAA sponsored inter-laboratory calibration studies and NOAA system audits.
The project QAC ensures that each QA officer has for each aspect of the
project performed adequate internal audits of performance and systems. The
NOAA Status and Trends Program director, based in Rockville, Maryland, will
perform a systems audit on an annual basis.
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Section No. 	12	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 1 of 1	
PREVENTIVE MAINTENANCE
Equipment maintenance is performed according to manufacturer's
recommendations and schedules. Equipment performance is documented in
instrument log books. Equipment is cleaned/serviced as necessary to maintain
optimal performance, as described under Internal Quality Control Check, (p.26).
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Section No. 	13	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 1 of 	1
CORRECTIVE ACTIONS
Corrective actions fall into two categories: 1) handling of analytical
or equipment malfunctions; and 2) handling of nonconformance or noncompliance
with the QA requirements that have been set forth. During field operations
and sampling procedures, the field supervisor will be responsible for
correcting equipment malfunctions. All corrective measures taken will be
included in the cruise log.
The QA officers listed in Section 4 are responsible for their respective
areas of involvement. Predetermined methodology, limits of acceptability, and
required sample handling are listed in this report. Corrective action
required to conform to the specifications will be recorded by the QA officer
and reported to the Project QAC within three days. Corrective actions will be
documented and included in the QA/QC report to the Program QAC.
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Section No. 	14	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 1 of 	2
REFERENCES
Abbey, S. (1980). Studies in "Standard samples" for use in the general
analysis of silicate rocks and minerals. Part 6: 1979 edition of "usable"
values, Geological Survey of Canada, Paper 80-14, 29 pp.
Baker, E.T. (1984). Patterns of Suspended Particle Distribution and Transport
in a large Fjord-like Estuary. Journal of Ceophysical Research, 89: 6533-
6566.
Baker, E.T. and H.B. Milburn (1983). An Instrument system for the
Investigation of Particle fluxes. Continential Shelf Research 1(4): 425-
435.
Baker, E.T. and D.Z. Piper (1976). Suspended particulate matter: collection
by pressure filtration and elemental analysis by thin-film X-ray
fluorescence. Deep-Sea Res., 23: 181-186.
Bates, T.S., S.E. Hamilton and J.D. Cline (1983) Collection of Suspended
Particulate Matter for Hydrocarbon Analyses: Continuous Flow Centrifugation
vs. Filtration, Estuarine, Coastal and Shelf Science 16: 107-112.
Bates, T.S., S.E. Hamilton and J.D. Cline (1984) Vertical Transport and
Sedimentation of Hydrocarbons in the Central Main Basin of Puget Sound
Washington, Environmental Science and Technology, 18: 299-305.
Eggimann, D.W. and P.R. Betzer (1976). Decomposition and analyses of
refractory oceanic suspended material. Analytical Chemistry 48(11): 886-890.
Feely, R.A., G.J. Massoth and W.M. Landing (1981a). Major and trace element
composition of suspended matter in the northeast Gulf of Alaska:
Relationships with major sources, Marine Chem., 10(15): 431-453.
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Section No. 	14	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 2 of 	2
Feely, R.A., G.J. Massoth, A.J. Paulson, M.F. Lamb and E.A. Martin (1981b).
Distribution and elemental composition o£ suspended matter in Alaskan coastal
waters, NOAA Technical Memorandum ERL PMEL-17, Seattle, WA., 119 pp.
Flanagan, F.J., ed., (1976). Descriptions and analysis of eight new USGS rock
standards. Geological Survey Professional Paper 840, 192 pp.
Hamilton, S.E., T.S. Bates, and J.D. Cline (1984) Sources and Transport of
Hydrocarbons in the Green-Duwamish River, Washington, Environmental and
Science Technology, 18: 72-79.
Holmes, G.S. (1981). The limitations of accurate "thin-film" X-ray
fluorescence analysis of natural particulate matter: problems and
solutions. Chem. Geol., 33: 333-353.
Ingle, J.D., Jr., and R.L. Wilson (1976). Difficulties with determining the
detection limit with nonlinear calibration curves in spectrometry. Analytical
Chemistry 48(11): 1641-1642.
Kingston, H.M., I.L. Barnes, T.J. Brady, T.C. Rains and M.A. Champ (1978).
Separation of eight transition elements from alkali and alkaline earth
elements in estuarine and seawater with chelating resin and their
determination by graphite furnace atomic absorption spectrometry. Analytical
Chemistry 50(14): 2064-2070.
Paulson, A.J. (1986). The Effects of Flow Rate and Pretreatment of the
Extraction of Trace Metals from Estuarine and Coastal Seawater by Chelex-
100. Anal. Chem. 58(1): 183-187.
Perkin-Elmer (1977). Analytical methods using the HGA graphite furnace.
Perkin-Elmer, Norwalk, Conn.
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Section No. 	15	
Revision No. 3 (November 1986)
Date November 01, 1986	
Page 1 of 2	
APPENDIX A
TRACE ORGANIC COMPOUNDS QUANTIFIED DURING THIS PROJECT
Phenanthrene (Phe)
Anthracene (Ant)
Methyl Phenanthrene (MPH)
(Four isomers)
Fluoranthene (FLa)
Pyrene (Pyr)
Retene (Ret)
Benzofluoranthene (BF1)
(Three-isomers)
DDE
DDD
DDT
Dichlorobiphenyls (CL2)
Trichlorobiphenyls (CL3)
Tetrachlorobiphenyls (CL4)
Benzo(e)pyrene (BEP)
Benzo(a)pyrene (BAP)
Indeno Pyrene (IPY)
Benzo(g,h,i)perylene (BPe)
Chrysene (Chr)
Benz(a)anthracene (BAA)
PentachlorobiphenyLs (CL5)
Hexachlorobiphenyls (CL6)
Heptachlorobipheyls (CL7)
Octachlorobiphenyls (CL8)
NonachlorobiphenyLs (CL9)
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