-------
TABLE C-38
Trident
No.
17-1
17-2
17-3
17-4
17-5
17-6
17-7
17-8
Sample
Type
sediment
sediment
sediment
sediment
sediment
sediment
sediment
sediment
Moisture
%
61.48
57.71
58.79
60. 14
74.43
48. 54
54. 18
54. 92
Total
Hydro-
Carbons
Hexane
Extract
mg/kg
8, 300
4, 300
1, 800
3, 300
18, 600
1, 500
< 100
<100
Metals mg/kg
As
50
32
34
45
184
13
13
12
Hg
0. 75
0. 44
0. 37
0. 36
1. 36
0. 52
0. 04
0. 09
Cd
2
3
2
2
8
<1
<1
<1
Cr
640
250
170
210
950
100
41
33
Cu
270
130
71
72
400
44
17
25
Mn
720
1, 300
1, 200
1, 100
390
660
720
1, 200
Ni
61
54
47
44
57
44
32
54
Pb
240
150
170
140
610
81
22
33
Zn
870
400
350
450
1, 800
120
100
100
o
-------
TABLE C-39
Trident
No.
18-1
18-2
18-3
18-4
18-5
18-6
18-7
18-8
Sample
Type
sediment
sediment
sediment
sediment
sediment
sediment
sediment
sediment
Moisture
%
65. 11
67.88
64. 91
66. 00
59.42
55. 22
58. 59
50.43
Total
Hydro-
Carbons
Hexane
Extract
mg/kg
16, 100
13, 100
10, 500
7, 400
2, 800
390
<100
1, 900
Metals mg/kg
As
108
116
103
150
77
10
6
10
Hg
0. 84
1. 15
1. 25
1.66
1. 30
0. 09
0. 05
0. 13
Cd
5
5
4
4
1
<1
<1
1
Cr
760
720
640
540
220
38
40
130
Cu
410
460
420
450
190
22
19
32
Mn
490
500
490
570
470
1, 900
2, 800
2, 300
Ni
65
61
53
56
61
41
43
53
Pb
300
320
350
400
280
29
30
28
Zn
1, 530
1, 740
1, 430
1, 060
400
83
92
100
o
I
-------
TABLE C-40
Trident
No.
19-1
19-2
19-3
19-4
19-5
19-6
19-7
Sample
Type
sediment
sediment
sediment
sediment
sediment
sediment
sediment
Moisture
%
61.62
58.23
59.79
57. 50
62. 19
54.73
53.32
Total
Hydr^-
Carbons
Hexane
Extract
mg/kg
4, 500
8, 000
7, 300
6, 200
6,400
820
3, 300
Metals mg/kg
As
63
73
74
101
63
9
14
Hg
0. 73
0. 81
0. 96
1. 08
0. 96
0. 36
0. 58
Cd
4
5
4
4
5
2
1
Cr
330
480
370
390
440
100
160
Cu
260
390
400
320
350
48
96
Mn
830
930
690
790
730
1, 000
730
Ni
78
63
76
95
95
42
45
Pb
220
280
200
180
300
48
84
Zn
660
1, 100
1, 050
1, 190
1, 290
150
170
n
Ul
-------
TABLE C-41
Trident
No.
20-1
20-2
20-3
20-4
20-5
20-6
20-7
20-8
Sample
Type
sediment
sediment
sediment
sediment
sediment
sediment
sediment
sediment
Moisture
%
62.81
61.25
66.70
58. 50
55.66
53.42
56.28
50.64
Total
Hydro-
Carbons
Hexane
Extract
mg/kg
8, 900
9, 700
13,400
17, 100
12, 700
10, 100
1,900
13, 800
Metals mg/kg
As
58
50
68
75
96
116
8
87
Hg
1. 21
1. 04
1. 34
1. 81
2. 85
1. 64
0. 09
2. 16
Cd
4
3
4
4
3
2
<1
3
Cr
450
410
650
610
340
250
73
290
Cu
390
290
460
470
550
300
55
750
Mn
510
390
390
390
350
510
610
200
Ni
62
81
68
71
70
63
62
47
Pb
290
210
230
530
420
230
48
310
Zn
210
620
1, 050
920
700
460
110
120
o
I
-------
APPENDIX D
POLYCHLORINATED BIPHENYLS
-------
D.I INTRODUCTION
Poly chlorinated biphenyls (PCB's) are aromatic organochlorine compounds
obviously named for their chemical structure, consisting of a biphenyl group
with ten available sites for chlorination.
PCB
X-CI
In normal manufacturing, PCB's are not isolated for marketing as single
compounds, but rather as a mixture of chlorinated biphenyls. Jensen (1970)
states that in theory, 189 different arrangements containing 1 to 8 chlorine
atoms are possible, but that in normal manufacturing, 4 to 8 chlorine atoms
attach to the parent biphenyl molecule (even with only 4 to 8 chlorine atoms,
there are 102 different molecular arrangements). Walker (1976) states that
there are 209 isomers in PCB mixtures and formulations.
Since single polychlorinated biphenyls are not isolated for marketing,
the degree of chlorination (as percentage by weight of chlorine) identifies
the commercial product. In the United States, PCB's are manufactured by
Monsanto Chemical Co., St. Louis, Missouri, with production somewhere between
15,900 to 38,600 metric tons per year (Walker, 1976) of Aroclor - the trade
name. Eight Aroclor formulations - 1221, 1232, 1242, 1248, 1254, 1260, 1262
and 1268 are marketed. The "12" designation defines the product as a PCB
while the last two digits (42, 48,-retc.) indicate the percentage by weight of
chlorine.
D-2
-------
Widespread use of PCB's started before 1930 (Penning, 1930). The
primary use of PCB's is in manufacturing electrical transformers and capaciters
although they are also used in marine anti-fouling paints, in cardboard
cartons, as dust-allayers, in insecticides, as plasticizers, as hydraulic
fluids, in protective coatings, as sealers, in inks, waxes and adhesives, in
thermostats, as lubricants, as grinding fluids and as sealers in electrical
applications.
The use of PCB's in the variety of applications previously mentioned
stems partially from their physical and chemical properties. Generally, low
vapor pressures, low water solubility, high dielectric constants, inertness,
stability at high temperatures, resistance to acids, bases and microbial
activity, and fat solubility characterize PCB's. Many of these characteristics,
especially fat solubility, inertness, and resistance to microbial activity-.
make PCB's persistent contaminants in the environment.
Although PCB's are widely used (their early development is documented
in Schmidt and Schultz, 1881), concern over their toxicity first appeared in
the 1930's when workers making PCB's developed certain pathologies (Jones and
Alden, 1936; Good and Pensky, 1943; Drinker et al., 1937; Flinn and
Jarvik, 1939; Greenberg et al., 1939; Schwartz, 1943; Schwartz and Barlow, 1942;
and Schwartz and Peck, 1943). However, PCB presence in the environment became
noticed when many investigators observed a series of unidentified peaks on
gas chromatograms (reviewed in Reynolds, 1971). Most of the samples were
pesticide residues especially from fish and raptors containing fairly large
concentrations of organochlorine pesticides (many pesticides such as DDT,
methoxychlor, etc. are quite similar to PCB's in molecular structure). Jensen
(1966) was the first to relate the unidentified peaks to PCB's. The problem
D-3
-------
of PCB interference with pesticide analyses is discussed in Reynolds (1971)>
Zitko (1972), Stalling and Huckins (1973), and Stalling et al. (1972).
After Jensen's (1966) initial confirmation of PCB's in wildlife, more
reports of PCB contamination followed as reviewed in Walsh (1972) , Reynolds
(1971), Dustman et al. (1971), and Walker (1976). Generally, these reports
continued to cover fish and raptors although some attention was beginning
to center on other species.
After observing high levels of PCB's in many animals, concern was
expressed over the possible toxicity of PCB's especially after Mclaughlin
et al. (1963) reported that Aroclor 1242 was toxic and teratogenic. Some
of these early studies are reviewed in Walsh (1972) , Reynolds (1971), and
Walker (1976) concerning toxicity and mode of action for PCB's.
Walker (1976) points out that high concentrations of PCB's occur con-
comitently with heavy industrial activity. In this study, an analysis is made
of sediments from Baltimore Harbor for the presence of two PCB's - Aroclor
1248 and Aroclor 1260.
D.2 PROCEDURES
A total of 20 stations (Fig. D-l ) within Baltimore Harbor were sampled
by a piston corer equipped with a 4.6 m polycarbonate liner. Two cores were
taken per station. Completion of coring took 6 days during 9 June to 15 June
1976.
Samples for PCB analyses were taken from the cores at four depths -
5 cm, 15 cm, 30 cm and 61 cm. Core material was removed with wooden applicator
sticks and immediately transferred to clean glass vials. Vials were sealed
by first capping with aluminum foil (acetone-washed) and then capping with
D-4
-------
plastic lids.
All samples were shipped to Analytical Bio Chemistry Laboratories, Inc.,
Columbia, Mo. for PCB analyses. A weighed portion of the air dried sample
was adjusted to approximately 20% moisture. Each sample was extracted with
methanol/chloroform (1:1) by blending in a Sorval Omni mixer. Following
filtration, the extract was diluted with water and the PCB's partitioned
into the chloroform. A series of repeated extractions and backwashings
removed the methanol from the chloroform phase. The chloroform was evaporated
and the residue subjected to Florisil column chromatography (20 g, 22 mm i.d.)
in which the PCB's were eluted with 200 ml of hexane. The eluant was
evaporated and transferred to a final volume of 5 ml. Microliter injections
into a gas-liquid chromatograph equipped with Ni,., electron capture detectors
were used for identification and quantification.
The GLC-EC parameters were: injector temperature - 225 C; column -
1.83 cm x 4 mm, 2% OV-210, 1.5% OV-17 on Chrom W 100/120, temperature 205 C;
and detector temperature - 300 C. Calculations were based on the middle
five peaks of Aroclor 1248 and the last nine peaks of Aroclor 1260 and
reported as ppm (w/w) air dried basis. A peak ratio judgement was made to
determine the species or peaks to be considered for identification and
quan ti fi cation.
A total of 80 samples were analyzed for Aroclor 1260 and 76 for Aroclor
1248. A 5 cm sample was not run for station 7 (Fig. D-l) . Duplicates were
run on station 8 - 5 cm depth.
Statistical procedures were from Sokal and Rohlf (1969). Calculations
were performed on a Canon F-20P statistical calculator.
D-5
-------
Figure D-l - Sampling (coring) stations for PCB analyses
within Baltimore Harbor
-------
BALTIMORE HARBOR
-------
D.3 RESULTS
PCB concentrations by depth for the 20 stations (Figure D-l) samples
are presented in Table D-l. High concentrations, greater than 1.0 ppm total
PCB's, are present at stations 1, 2, 3, 4, 5, 10, 15, and 18. Gross contamination
of the upper sediments occurs at station 1 where PCB concentrations approach
84.2 ppm and remain high throughout the sediment column. Generally, stations
1, 2, 3, 4, 5, and 15 contain.extremely high PCB levels, especially in the top
30 cm of the core.
Stations 6, 8, 9, 12, 13, 14, 16, 17, 19, and 20 are classified as being
intermediately contaminated since their PCB concentrations are less than
1.0 ppm and greater than 0.05 ppm total PCB's. Station 6 has intermediate
levels of PCB's in the upper 5 cm of the sediment, but concentrations drop
with increasing depth.
Station 20 did not have detectable PCB's in the upper 5 cm of the sediment
column, but intermediate concentrations of PCB's are present below 15 cm.
There is a possibility that recent scouring and dredging or a discontinuation
of PCB input may have occurred at this station.
At stations 7 and 11, PCB concentrations are less than 0.05 ppm. Both
of these stations are located in the outer harbor area near the reference
station 12.
Generally, there is a decrease in PCB concentration with -sediment depth.
Besides station 20, stations 9, 14 and 19 did not follow the pattern of lower
PCB concentrations with depth. For three stations (4, 7S -11, and 12) no apparent
pattern (within statistical limits) of PCB's exist. Eleven of the remaining
stations, within statistical range, show decreasing PCB levels with sediment
depth.
D-8
-------
TABLE D-l
PCB concentrations (ppm w/w basis) for Baltimore Harbor stations
(Figure D-l) by depth.
Station Depth (ft) Depth (on)
I1 0.16
0.5
1.0
2.0
2 0.16
0.5
1.0
2.0
3 0.16
0.5
1.0
2.0
4 0.16
0.5
1.0
2.0
5 0.16
0.5
1.0
2.0
6 0.16
0.5
1.0
2.0
5
15
30
61
5
15
30
61
5
15
30
61
5
15
30
61
5
15
30
61
5
15
30
61
Aroclor 12,60
84.19
2.41
0.59
3.11
1.26
0.91
0.60
0.32
1.70
0.97
0.89
0.71
0.84
0.94
0.80
0.71
2.10
1.20
0.24
0.05
-0.10
<0.05
<0.05
<0.05
D-9
Aroclor 1248
0.87
0.54
0.39
0.13
0.57
0.76
0.76
0.64
0.51
0.71
0.39
0.55
3.50
1.50
0.14
< -0.05
0.11
<0.05
<0.05
<0.05
Total
>84.19
> 2.41
> 0.59
> 3.11
2.13
1.45
0.99
0.45
2.27
1.73
1.65
1.35
1.35
1.65
1.19
1.26
5.60
2.70
0.38
> 0.05
0.21
<0.05
<0.05
<0.05
-------
TABLE D-l
PCB concentrations (ppm w/w basis) for Baltimore Harbor stations
(Figure D-l) by depth, (continued)
Station Depth (ft)
7 0.5
1.0
2.0
8 0.16
0.16
0.5
1.0
2.0
9 0.16
0.5
1.0
2.0
10. 0.16
0.5
1.0
2.0
11 0.16
0.5
1.0
2.0
12 0.16
0.5
1.0
2.0
Depth (cm)
15
30
61
5
5
15
30
61
5
15
30
61
5
15
30
61
5
15
30
61
5
15
30
61
Aroclor 1260
<0.05
<0.05
<0.05
0.16
0.15
0.06
<0.05
<0.05
0.41
0.12
0.64
0.14
0.29
0.17
0.19
0.17
<0.05
<0.05
<0.05
<0.05
<0.07
0.06
<0.05
0.07
D-10
Aroclor 1248
<0.05
<0.05
<0.05
0.11
0.22
0.07
<0.05
<0.05
0.23
<0.05
0.32
0.06
0.83
0.29
0.24
0.16
<0.05
<0.05
<0.05
<0.05
<0.05
<0.05
<0.05
0.11
Total
<0.05
<0.05
<0.05
0.27
0.37
0.13
<0.05
<0.05
0.64
0.12
0.96
0.20
1.12
0.46
0.43
0.33
<0.05
<0.05
<0.05
<0.05
>0.07
>0.06
<0.05
0.18
-------
TABLE D-l
PCB concentrations (ppm w/w basis) for Baltimore Harbor stations
(Figure D-l) by depth, (continued)
Station Depth (ft) Depth (cm)
13 0.16
0.5
1.0
2.0
14 0.16
0.5
1.0
2.0
15 0.16
0.5
1.0
2.0
16 0.16
0.5
1.0
2.0
17 0.16
0.5
1.0
2.0
5
15
30
61
5
15
30
61
5
15
30
61
5
15
30
61
5
15
30
61
Aroclor 1260
0.32
0.33
0.30
<0.05
0.06
<0.05
<0.05
0.10
1.48
0.55
0.25
<0.05
0.10
0.07
0.05
<0.05
0.47
0.57
0.06
0.08
Aroclor 1248
0.28
0.14
0.11
<0.05
0.06
<0.05
<0.05
0.07
0.84
1.32
0.14
0.05
0.09
0.06
<0.05
<0.05
0.31
0.19
<0.05
0.10
Total
0.60
0.47
0.41
<0.05
0.12
<0.05
<0.05
0.17
2.32
1.87
0.39
0.05
0.19
0.13
0.05
<0.05
0.78
0.76
0.06
0.18
D-ll
-------
TABLE D-l
PCB concentrations (ppm w/w basis) for Baltimore Harbor stations
(Figure D-l) by depth. (continued)
Station
18
19
20
Depth (ft)
0.16
0.5
1.0
2.0
0.16
0.5
1.0
2.0
0.16
0.5
1.0
2.0
Dep th ( cm)
5
15
30
61
5
15
30
61
5
15
30
61
Aroclor 1260
0.61
0.22
0,14
0.08
0.06
0.22
0.17
0.25
<0.05
0.28
0.23
0.12
Aroclor 1248
0.64
0.23
0.15
<0.05
0.05
0.25
0.21
0.28
<0.05
0.43
0.12
0.10
Total
1.25
0.45
0.29
0.08
0.11
0.47
0.38
0.53
<0.05
0.71
0.35
0.22
Aroclor 1260 was masking 1248 values so that total values may be
substantially higher for this one sample set.
D-12
-------
In Figure D-2, PCB concentrations for the Baltimore Harbor stations are
plotted as a function of depth and channel length (in kilometers). It
is obvious, except for the PCB concentrations at station 20, that from station
1 to 18, high PCB loading is present in the sediments. A localized high con-
centration of PCB's is observed at stations 5 and 15.
From station 9 to 6 (Figure D-2) and except for stations 18 & 16,
total sediment PCB concentrations are greater than 0.05 ppm but less than
1.00 ppm. At stations 7 and 11, PCB's have essentially disappeared from the
sediment (no values are available for station 7 at the 5 cm level). PCB's
are also starting to disappear at the lower depths from stations 8 to 11.
In Figure D-3, the relationship of Aroclor 1248 to 1260 concentrations is
plotted. There is a significant (at p<0.001, r=0.91) correlation between
1248 and 1260 values in the sediments. Three significant outliers occur.
At station 3, the level of 1260 is over three times greater than the 1248 value.
At station 15 for the 15 cm depth, the 1248 concentration is almost 2.5
times greater than the 1260 concentration. At station 10, the 1248 value is
also 2.5 times greater than the 1260 value at the 5 cm depth. These factors
may be a result of industrial usage patterns.
D.4 DISCUSSION
Sediment concentrations of PCB's except for special cases at station
20 (low level) and stations 5, 15, ajid 18 (high levels) tend to be elevated from
station 19 to station'1 - the inner seven kilometers from approximately Colgate
Creek through the Northwest Branch. From station 9 (Curtis Bay) to station 12
(Old Road Bay), PCB concentrations are greater than 0.05 ppm, but less than
1.00 ppm of total PCB's. Outside of the entrance to the harbor, PCB
D-13
-------
Figure D-2 - PCB concentrations as a function of depth and channel
length in Baltimore Harbor. Dark shading indicates PCB
concentrations greater than 1 ppm, lateral markings indicate
PCB concentrations less than 1 ppm but greater than 0.05 ppm,
and clear areas indicate PCB concentrations less than 0.05 ppm,
-------
1 2 10 3 20
STATION
4 19 9 18 17 58 15 16
14 7 13 6 11 12
10
KILOMETERS
15
-------
Figure D-3 - The relationship of Aroclor 1248 to Aroclor 1260
concentrations (in ppm) in sediments from Baltimore
Harbor. Paired values or single values less than 0.05
ppm PCB's were not used in the analysis.
-------
TJ
H-
C
ro
a
10
a.
I
oo
CN
U
O
CtL
O
.4
.8
AROCLOR
1.0
1260 - PPM
1.2
1.6
1.8
-------
concentrations drop to levels below 0.05 ppm (station 12 has low PCB levels,
but primarily 1260 appears in the samples). Two factors may account for the
accumulation of increased levels of PCB's in Baltimore Harbor. Obviously,
PCB's have been released into the water in the past. First there is the
possibility of present releases still being made into the harbor with PCB's
being entrapped into the sediment column. Second, current patterns in
Baltimore Harbor may tend to contain pollutants within the harbor confines.
A unique three-layered circulation system (Pritchard, 1968) in Baltimore
Harbor may minimize transport of material out of the area.
The predominance of Aroclor 1260 over 1248 is also of interest. Either
more 1260 is in use in Baltimore Harbor or some of the 1248 is being slowly
lost since the lower Aroclors are more readily biodegradable (Walker, 1976):.
Walker (1976) points out that for systems where a variety of Aroclors are
present, it is more important to measure PCB's as a sum of the chloro-homo-
logs (mono, di, etc.) rather than as 1242, 1248, 1260, etc.
PCB contamination tends to be associated with industrialization or
with accidents. Walker (1976) points out that PCB residues in fish are high
in heavily industrialized riverine systems. Koo (1975) points out that over
170 potential sources of industrial wastewaters are present in Baltimore
Harbor with two major sewage treatment plants (a possible source of PCB's since
chlorination is a standard operating procedure) discharging 76,000 m-Vday of
treated sewage into Baltimore Harbor. In a summary section, Koo (1975)
also points out that environmental stress is present, with semi-healthy
conditions at the mouth and polluted conditions in the inner harbor area.
Pfitzenmeyer (1975) summarizes the available literature on the pollution of
Baltimore Harbor. Heinle and Morgan (1972) and Morgan et al. (1973) discuss
the sublethal effects of Baltimore Harbor water on a variety of organisms.
D-18
-------
The input of PCB's into estuarine waters is the result of a variety of
processes (Walsh, 1972) - (1) agricultural runoff, (2) industrial/
municipal discharge, (3) drift and rainfall and (4) accidental/careless
discharge. Although PCB's are relatively insoluble in water, they may be
made soluble by humic acids as occurs with pesticides (Wershaw et al., 1969).
PCB transport may come not only from water movement, but also from the involved
process of sediment flocculation and resuspension - a phenomena in the
estuarine system. In addition, differential solubilities of PCB's may result
in precipitation (Walsh, 1972). No matter what the level of PCB input may
be to a system, the possibility exists that biomagnification and bio-
accumulation could occur to an extent which could be damaging to a population
or to the entire aquatic community.
Any analysis of PCB accumulation'in sediments is complicated by the
relative insolubility of the different formulations. Most of the crystalline
PCB's are insoluble, however, resinous and liquid PCB's solubilize in
organic solvents,' thinners and oils (Reynolds, 1971). For oceanic waters,
90% of the PCB's are dissolved (Harvey, unpublished data in Duce et al.,
1974).
Sediments appear to be a pool for PCB's in estuarine and marine systems
(Duce et al., 1974) with concentrations of sediment PCB's inversely pro-
portionate to water depth. Harvey (unpublished data, Duce et al., 1974)
found PCB concentrations ranging from 500 ng/g sediment (ppb) in inshore
Massachusetts to 0.3 ng/g sediment in uie Hatteras Plain. For San Francisco
Harbor, PCB's range from 0.026 to 0.833 ppm (Pacific Northwest Laboratories,
1974). Duke et al. (1970), investigating an industrial spill of Aroclor
1254, found sediment containing up to 486 ppm of PCB's.
Horn et al. (1974) observed PCB deposition rates of 1.2 x 10~^ 5/m2/year
D-19
-------
in the Southern California Bight.
Given either a value for sediment or water PCB content, what are the
possible concentrations of PCB's in estuarine populations or communities.
Although some detailed analyses of ocean water have been made, very few
studies have been concerned with transfer mechanisms of PCB's in estuarine
and coastal systems where major ecological effects could occur (Duce et al.,
1974). An organic may become present in very low quantities within an
aquatic community. Based on a variety of factors such as salinity, sediment/
solution ratio, and concentrations, PCB's may accumulate in populations
and communities. It appears that chemical and some physical factors such
as temperature, pH, Eh, and dissolved oxygen are not important when dealing
with PCB desorption from sediments. Initially, a primary producer or hetero-
troph will take up the toxic material from either the water column or from
deitrus and suspended sediments. Primary consumers will further concentrate
toxic materials. Eventually, upper components (fish, mammals, birds, etc.)
of an aquatic ecosystem will concentrate the material 10 to 10 - fold.
Within a population, the problem is bioaccumulation, within a community
the problem is biomagnification. Bioaccumulation or biomagnification of
toxic materials may reveal itself in two ways - acute effects and sublethal
effects. Acute effects, such as mortality and increased vulnerability to
predation, could occur. Sublethal effects, by definition, are the typical
consequence of biomagnification and bioaccumulation in aquatic communities.
Bioaccumulation in a population is directly related to the lipophylicity
of PCB's and the overall bioenergetics of the population (Norstrom et al.,
1976). Strongly lipophylic agents will probably be assimilated at maximal
or near-maximal efficiency. Thus, the uptake rate of these residues will
fall within limits set by populational characteristics such as metabolic
D-20
-------
rate and growth, which in turn are a function of the environmental variables
acting on that population (Norstrom et al., 1976).
The level of a residue within a single organism of a population is a
function of exposure, dose and absorption of the residue into the organism.
Within the organism, the concentration becomes a function of residue dis-
tribution, deposition, remobilization and excretion. For lipophylic
compounds, prime areas of deposition are organisms such as fish, mammals
and birds.
Wildish and Zitko (1971) propose that PCB uptake may be accomplished
by either absorption in the gut from food or water or through the body surface.
Harvey et al. (1974) find PCB concentrations in Atlantic plankton ranging
from 200 pg/kg to 100 yg/kg wet weight - samples with high PCB concentrations
contained large numbers of phytoplankton. Duce et al. (1974) report that
unicellular algae can concentrate ng/g quantities of PCB's as much as ten-
thousandfold. However, herbivores feeding on the same algae could only
accumulate PCB's two- to fivefold; larval fish also could only accumulate PCB's
two- to fivefold from feeding on the herbivores (Duce et al., 1974). However,
sediment-feeding invertebrates living in an area of high PCB's could easily
ingest large quancities of PCB's. This may shorten the link between the
higher trophic levels.
Wildish and Zitko (1971) find that PCB uptake in amphipods increases
with increasing PCB concentration although the rate of uptake decreases
after 4 to 6 hours exposure. Sanders and Chandler (1972) note that bio-
accumulation in invertebrates for short term exposures range from 160 to
6,300 times the water concentration, but bioaccumulation in longer exposures
results in PCB accumulation from 27,000 to 48,000 times the water con-
centration. In fish (Hansen et al., 1971) accumulation rates occur at
D-21
-------
10,000 to 50,000 times the environmental levels. Vreeland (1974)
points out, in a series of experiments with oysters, that PCB's containing
more chlorine atoms (such as 1260) accumulate in greater amounts. Based
on Vreeland's data, it was calculated the correlation of degree of chlorination
versus the log of the equilibrium isomer concentration and found a highly
significant (r=0.97) relationship between the numbers of chlorines on the
parent biphenyl and isomer concentration in oysters. For any increase of
1 pptr in the water, oysters accumulate 1-2 ppb for the dichloro isomer
to 48 ppb for the hexachloro isomer (Vreeland, 1974). Generally, Vreeland
(1974) reports equilibrium of PCB content in oysters with environmental
conditions approximately one month after exposure. In Florida, Duke et al.
(1970) found that many estuarine species accumulated 1254 in amounts from
1.0 to 184 ppm with a sediment concentration of 486 ppm (maximum).
Although high concentrations of PCB's do accumulate in mammals, fish
and birds, many factors such as lipid content, degree of chlorination,
physical and chemical factors, etc. may determine actual PCB concentrations
in aquatic food webs. Norstrom et al. (1976) have developed a model for
pollutant accumulation based on pollutant biokinetics linked to fish
energetics. The uptake rate of pollutants is dependent on both species-
specific factors (metabolism, growth, lipid content, etc.) and environmental
factors (salinity; temperature, food, etc.).
As described before, bioaccumulation is a populational characteristic
(really an individualistic phenomena). Once a pollutant is part of a living
organism, concern then shifts to the problem and process of biomagnification
through food webs and trophic assemblages, Biomagnification is obviously
important, in relation to human health, if the upper components of the food
D-22
-------
chain are accumulating PCB's in large enough amounts to cause damage upon
human consumption.
Of equa."". importance to the problem of human health, is the effect of
PCB's on community structure and function. Moore and Harriss (1972) found
that radiocarbon uptake by the phytoplankton is strongly inhibited at 5 ppb
of Aroclor 1242 and 1254 affecting lower trophic dynamics. In a related paper,
Mosser et al. (1972) noted that competitive interactions between two species
of algae are altered at PCS concentrations as low as 1 ppb. Nebeker et al. (1974)
studied the effect of PCB's on fish reproduction and survival; found growth
and reproduction still occurring at and below 1.8 ppb of 1254 and at or below
5.4 ppb 1242. In their study, the newly hatched larvae were extremely
sensitive to 1254 and 1242. Growth of the larvae was affected at PCS levels
greater than 2.2 ppb. In a related study, Schimmel et al. (1974) studied
effects of 1254 on sheepshead minnows and found poor survival of fry at PCB
concentrations at or above 0.1 ppb, although embryos developed at 10.0 ppb.
The above studies point out that PCB's may affect community structure by
affecting growth and reproduction.
Obviously, PCB's are toxic, but are usually less toxic than compounds
such as DDT and dieldrin (Walsh, 1972). Generally in aquatic systems, toxicity
due to a substance is rarely observed. However, sublethal effects of that
toxicant are more important especially if the compound is an accumulator with
a long biological half-life.
Toxicity of PCB's is reviewed by Dustman et al. (1971), Fishbein (1974),
Walsh (1972), Walker (1976) and Reynolds (1971). At present, the majority
of PCB toxicology still deals with mammals and birds, although more emphasis
is being placed on aquatic organisms.
On a sublethal basis, PCB's tend to produce a variety of pathological con-
D-23
-------
ditions in man and rats including a variety of changes in hepatic function
(Allen and Abrahamson, 1973). PCB's are embryolethal, teratogenic and
carcinogenic plus also being immunosuppressive (Fishbein, 1974). Other
sublethal effects are associated with community and populational processes
such as growth, reproduction and competition (Moore and Harriss, 1972;
Mosser et al., 1972; Nebeker et al., 1974; Schimmel et al., 1974; Nebeker
and Puglisi, 1974). Risebrough et al. (1968) observed that only a few molecules
of chlorinated hydrocarbons are needed for steroid breakdown - an important
point when dealing with testicular and ovarian function or normal endocrine
pathways in aquatic animals.
Given the above information and the data from this study, what are the
possible relationships of PCB levels in Baltimore Harbor sediments to plants
and animals on a local basis. First, there are some assumptions before
the analysis. One, the water concentration of PCB's is in some equilibrium
with the sediment concentration. Second, the organism is neither hyper- nor
hyporich in lipid concentration. Third, each organism has an equal probability
of accumulating PCB's based on populational and physiological attributes
inherent for that species. Fourth, the organisms are exposed long enough
to take up PCB's to equilibrium.
For this analysis, information from three studies is required (Duke et
al. , 1970; Forns, 1972; and Munson, 1972). Duke et al. (1970) found 486 ppm
of 1254 in sediment and from 1.0 to 184 ppm in a variety of fish and in-
vertebrates. In this case, the animal to sediment ratio varies from 0.0021
to 0.379. Munson (1972) observed 1242 concentrations in Chester River sed-
iments ranging from 0 to 300 ppb with average values from 53 to 110 ppb.
(Munson also observed that PCB's bind to the sediment with an inverse relation-
D-24
-------
ship of concentration to particle size.) In the biota, Munson (1972)
observed (averages) for oysters - 55 ppb, clams - 58 ppb, fish - 185 ppb
and crabs - 20 ppb. Using a mean value of 87 ppb for Chester River sediment
PCB concentrations, the animal to sediment ratio varies from 0.22 for crabs,
0.63 for oysters, 0.66 for clams and 7.2 for fish. Forns (1972) found PCB
levels of 286 ppb of 1242 and 79 ppb of 1254 in plankton (primarily zooplankton
and values are maximum possible values). For zooplankton, the animal to
sediment ratio is 4.2.
Consider two areas of Baltimore Harbor, the inner heavily contaminated
area with sediment PCB concentrations greater than 1000 ppb and the other
areas with PCB's greater than 50 ppb. For zooplankton in the inner harbor,
PCB's may accumulate up to 4200 ppb. Fish may accumulate 2200 ppb, clams -
660 ppb, oysters - 630 ppb and crabs 200 ppb. Using the data from Duke,
accumulation would range from 2.1 to 379 ppm. In areas with sediment PCB levels
m
of 50 ppb, zooplankton would accumulate 210 ppb, fish - 110 ppb, clams -
33 ppb, oysters - 32 ppb and crabs - 11 ppb.
Based on the"sublethal information now known, it appears that PCB levels
in inner Baltimore Harbor are high enough to cause serious problems in both
population dynamics and community structure. Emphasis should now be placed
on monitoring actual PCB levels in organisms from Baltimore Harbor.
D.5 SUMMARY
Polychlorinated biphenyls were assayed in sediment cores (at four depths)
from 20 stations in Baltimore Harbor. Assay techniques included PCB extration
and detection through electron capture gas-liquid chromatography. Eighty
Aroclor 1260 and 76 aroclor 1248 samples were run. PCB concentrations were
high (greater than 1.0 ppm total PCB's) at stations 1, 2, 3, 4, 5, 10, 15, and 18.
D-25
-------
The highest level was 84.2 ppm of aroclor 1260 at station 1 in the Inner
Harbor area. Heavy concentrations of PCB's (5.6 ppm) were also observed at
station 5 in Bear Creek. Non-existant or low quantities of PCB's were
observed at stations 7 and 11 with low levels at stations 6, 8, 12, 14, and 16.
Generally, high levels of PCB's correlated to large amounts of hexane extractable
total hydrocarbons.
Levels of PCB's within the Inner Harbor area as well as Colgate and
Bear Creeks are high enough to cause significant biological effect if exposure
to the PCB-laden sediments is of a long enough duration.
PCB soluability is low in water and higher in oils and fats. The coincidental
occurrence of PCB's and hexane extractable materials at some stations strongly
suggests that exceptional care must be taken in handling materials from such
sites to preclude significant PCB pollution at areas of sediment placement.
D-26
-------
APPENDIX E
BIOASSAY OF
BALTIMORE HARBOR SEDIMENTS
-------
E. 1 LITERATURE REVIEW
Literature pertaining to the biology of Baltimore Harbor prior to 1971
was reviewed briefly by H. T. Pfitzenmeyer (Center for Environmental
and Estuarine Studies, 1975). He stated that natural resources of the
Harbor rapidly declined before the turn of the century. There were
3,800, 000 square yards of oyster bars within the Harbor, northwest
of a line from Old Road River to Sellers Point, in 1884. In 1907 the
northern limit of all oyster grounds was Rock Point at the entrance to
the Harbor, and bottoms above Bodkin Point were not recommended for
oyster culture. Yates (1913) made a survey of oyster bars in Chesapeake
Bay in 1906-1912, and no oyster bars were shown for Baltimore Harbor.
Olson, et al, (1941) studied the effects of industrial pollution of copperas,
Fe (OH)^, on the biological productivity of Curtis Bay and nearby water
in Baltimore Harbor. This red-brown precipitate appeared to decrease
dissolved oxygen concentration of water during the summer, affecting
plankton by asphyxiation and then indirectly affecting higher organisms.
In a laboratory study, the floe of copperas caused a heavy coagulum on
gills of killfish (Fundulus), silversides (Menidia), and white perch
(Morone americana). They believed that this red-brown precipitate accu-
mulated on the bottom and contributed to a marked ecological disturbance
E-2
-------
of the area. Later; Davis (1948) also studied this copperas-polluted
area of Curtis Bay and confirmed the Olson, et al, (1941) findings; but
he found more diatoms present per liter in the polluted area than in the
relatively unpolluted area.
Weiss (1950) investigated the possibility of an outbreak of marine wood
borers caused by a reduction in pollution of Baltimore Harbor. No
molluscan or crustacean borers were found in the Harbor. Of the three
species of wood borers occurring in this latitude, sporadic sets by
Bankia gouldi might occur. Salinities were too low for Teredo navalis
and Limnoria lignorum. There was no evidence supporting the belief
that a reduction in pollution of the Harbor will increase shipworm
infestation.
Garland (1952) made the first extensive water quality survey of Baltimore
Harbor and the Patapsco estuary. He stated that in some seasons of the
year fishing was good at the entrance to the Harbor, but within the Harbor
fishing and crabbing diminished during the previous quarter of a century
and had virtually stopped. This, he concluded, resulted from waste
discharges.
E-3
-------
Stroupe, et al, (1961) investigated the physical hydrography of Baltimore
Harbor to determine the flushing rate and hydrographic mechanisms of
the Harbor. They suspected that fish and other animals were probably
not affected by the range of pH which occurred in the Harbor, and that
any deleterious effects might have resulted from increase in carbon
dioxide. However, high carbon dioxide concentration was favorable for
the growth of phytoplankton and marine plants.
Hohn and Hellerman (1966) studied diatoms in Lewes-Rehoboth Canal,
Delaware, and Baltimore area of Chesapeake Bay. They described four
new species from Curtis Bay, a major tributary of the Harbor, in the
vicinity of Sledds Point. These were Diploneis hormopunctata, Navicula
agmastriata, N. cumvibia and N. taraxa.
Chesapeake Biological Laboratory (Center for Environmental and
Estuarine Studies, 1975) conducted a comprehensive biological study of
Baltimore Harbor in 1970-1971. Four major biological groups were
studied: fish eggs and larvae by W. L. Dovel; invertebrate benthos
by H. T. Pfitzenmeyer, adult fish by M. L. Wiley, and blue crabs by
R. L. Lippson and R. E. Miller. The results were summarized and
edited by T. S. Y. Koo. It was found that the water column in Baltimore
Harbor still supported many species of fish, but the bottoms were unfit
for ground fish and for many species of benthic macro-invertebrates.
E-4
-------
Dyer (1971) of the Maryland Fish and Wildlife Administration investi-
gated fish kills of Bear Creek on September 16, 1971; and Riggin (1972)
of the Maryland Water Resources Administration investigated -water quality
of effluents and offshore waters at Bethlehem Steel Corporation Sparrows
Point Plant. Heavy metals were found in toxic concentrations in water
off Sparrows Point and cited as a major contributing factor for fish
kills in Bear Creek. Acids, caustics, cyanides, ammonia, and phenol
v/ere also detected in acutely toxic levels in the Harbor water.
Villa and Johnson (1974) of the Environmental Protection Agency's
Annapolis Field Office, Region III, studied the heavy metal contamination
of Baltimore Harbor sediments. They indicated that heavy metal contam-
ination might be a major contributing factor to the biological deterioration
of benthic communities of the Harbor.
Maryland Environmental Service (1974) studied the water quality of the
Harbor from 1968 to 1971 and produced a Draft Report. In this project,
the phytoplankton were studied by G. A. Bowman, St. Mary's College
of Maryland; and chronic bioassay of the Harbor water on clams, cope-
pods and fish was conducted by D. R. Heinle and R. P. Morgan, Chesa-
peake Biological Laboratory. Chlorophyl ji concentration and biomass
suggested that the Harbor was not highly eutrophic but that the phyto-
E-5
-------
plankton community was less diverse than that in the Chesapeake Bay.
The results of chronic bioassay showed that there were some effects
of the Harbor water on the survival of clams (Macoma balthica) and
inhibitory effects on brain acetylcholinesterase activity in two species,
the hogchoker (Trinectes maculatus) and the white perch. Otherwise,
there was no clear indication of damaging effects. The same report
indicated that fishermen were observed in the Inner and Outer Harbor
and on the Patapsco River bridge. In 1972, a 28-pound bluefish was
taken at Ft. Smallwood in the Outer Harbor and won the Sun Paper's
Annual Sport Fishing Contest.
Morgan, et al, (1976) studied antibiotic resistant bacteria in the Upper
Chesapeake Bay. Of nine water sampling stations, three stations were
located in Baltimore Harbor. The results showed a three-fold or greater
increase in the number of antibiotic resistant coliforms, extending up
the Bay from the Chesapeake Bay bridge north to Baltimore Harbor. The
increase in number of antibiotic resistant bacteria in the Harbor and its
vicinity suggested that sewage effluents had a detectable influence on
water quality.
E-6
-------
E. 2 INTRODUCTION
Baltimore Harbor receives great amounts of domestic and industrial
wastes from the City of Baltimore (Maryland Environmental Service,
1974). The Harbor sediments have been known to contain high concentra-
tions of organic silts (Center for Environmental and Estuarine Studies,
1975), volatile solids, mainly oil and grease (Garland, 1952), ferric
hydroxides (Olson, et al, 1941; Davis, 1948), and iron and heavy metals
(Villa and Johnson, 1974). Iron sulfate contributes a large portion of the
total industrial discharge to the Harbor (Garland, 1952). Chemical
constituents and toxic contaminants of the polluted sediments of Baltimore
Harbor are extremely complex, and their total chemical load and pollu-
tion load are not known. It is impossible to select a small number of
chemical parameters for a conventional chemical test, such as a bulk
test or the recently developed elutriate test, for determining the toxic
level of such sediments. In order to determine the toxic level of the
Harbor sediments, Lee and Plumb (1974) suggested that a sediment bio-
assay be made.
For this study, a bioassay was designed for determining the total bio-
logical impact of sediments from a set of stations widely distributed over
the Harbor system and including stations of known high pollution load and
E-7
-------
of relatively low load. Since only a partial chemical analysis could be
conducted at each site, it is impossible to assign with certainty the cause
or causes of biological damage, although some coincidences could be
considered. Such a bioassay series determines the range of toxicities
likely to be found, provides a ranking of the biological threat in various
locations, and suggests the more extensive research which would be
required for full quantification of effects and determination of their pre-
cise chemical or physical causes. The objectives of this study were:
(1) to determine gross toxicity of representative Harbor sediments for
several appropriate organisms; (2) to supplement the chemical data of
the Harbor sediments to further define and describe the problem areas
of the Harbor; and (3) to suggest the possible environmental effects of
dredging or other corrective actions.
E. 3 PROCEDURES
Nine sediment sampling stations were designed, representing the various
polluted parts of Baltimore Harbor noted in earlier studies (Figure E-l).
At each station, about thirty gallons of sediment was collected on
June 9, 1976 from the top one foot of bottom material. Salinity and
water temperature at the time of sampling are shown in Table E-l. Of the
total sample, about a half-gallon was removed for bulk chemical analyses
E-8
-------
.. MIDDLE: '£>'££A/Ctf.
'
O 'SAMPLE-, sir EX.
Q)'BIOA55AY &L& S1TLS
Figure E-l
E-9
-------
TABLE E-l
SALINITY AND TEMPERATURE OF WATER
AT THE SEDIMENT SAMPLING STATIONS
IN BALTIMORE HARBOR ON JUNE 9, 1976
Station
1
2
4
5
6
7
8
9
10
Site
—
B ott om
Surface
Bottom
Surface
Bottom
Surface
Bottom
Surface
Bottom
Surface
Bottom
Surface
B ott om
Surface
B ott om
Surface
Time
—
1305
—
1530
—
—
1730
1800
—
Temperature
°C
—
22.63
23.94
20.78
25.80
26.71
28.22
21.83
24.50
23. 18
26. 07
26. 07
26. 58
22.06
25. 15
21.87
27.39
Salinity
ppt
—
5. 42
5. 36
7. 78
4. 60
4. 20
3. 22
5. 37
2. 92
5. 26
4. 16
5. 03
4. 22
5. 72
5. 02
5. 12
3. 83
E-10
-------
of heavy metals, sediment moisture and hexane extracts. The rest of
the sample was brought back to the laboratory and kept hydrated in
anaerobic condition in the cold room at 4° C (Bricker, 1975). This
sediment sample was used as experimental material in fish bioassay.
Non-toxic fuller's earth was used as a reference material.
Sea water of five ppt salinity, about the mean salinity of the Harbor water
(Garland, 1952; Skelly, 1973), was made by mixing synthetic sea salts
with dechlorinated, aged tap water. This water was used as diluting
water for the sediments and control water in the study.
Two species of fish and one species of clam found in Chesapeake Bay
were used as test organisms. They were mummichogs (Fundulus
heteroclitus), spot (Leiostomus xanthurus) and soft-shell clams (Mya
arenaria). Mummichogs were collected from the Patuxent River estuary
about five miles upstream from Solomons, Maryland, Spot were collected
from the Patuxent River about a quarter mile downstream from the
Rt. 321 bridge. Soft-shell clams were also collected from the Patuxent
River near Solomons by Dr. R. Morgan and had been held in a Bay
water circulation tank for nearly a year at Chesapeake Biological
Laboratory.
E-ll
-------
These three test species were brought back to the laboratory and
acclimated in 5 ppt synthetic sea water for a week prior to the experi-
ments. Acclimation temperature was 25°C for mummichogs and spot
and 21°C for shoft-shell clams. The sizes of the test organisms were
43. 05 t 1. 39 mm (mean 1 standard errors) for mummichogs, 64. 95 I
4. 19 mm for spot, and 31. 08 t 0. 72 mm for soft-shell clams.
Four sets of static bioassay apparatus, each in 4' x 8' x 18" water bath,
were set up. Each set had six 10-gallon test tanks. Each tank contained
a 6" x 10" x 12" screen basket with a quarter-inch mesh to hold the test
organisms and a —— horsepower submerged pump to stir the sediment-
water mixture during the experiments. There was a space of about an
inch between the bottom of the basket and the bottom of the tank. The
pump was located at one end of the tank outside of the screen basket.
In order to prevent sediment settlement on the tank bottom, the mixture
was shot from the pump along the tank bottom surface to the other end
of the tank and then the mixture flowed upward and backward into the
screen basket. The test temperatures were the same as the acclimation
temperature.
E-12
-------
When a sediment sample at a station was to be used, the total sample
was taken out of the cold room and stirred with a wooden paddle. After
it was homogeneously mixed, about 10 gallons of the sediment was
removed and mixed with 20 to 30 gallons of the synthetic sea water to
make a stock sediment-water mixture. For each experiment, five dif-
ferent concentrations of the test sediment-water mixture were made from
this stock sediment-water mixture by mixing to the desired dilution with
the synthetic sea water in five test tanks. The sixth tank was filled -with
synthetic sea water and used as the control. Each tank contained 22 liters
of the sediment-water mixture. The test sediment-water mixture and
control water were stirred and aerated for at least 24 hours until the
color of the mixture changed from black into grayish brown to eliminate
high oxygen demands and to maintain an adequate dissolved oxygen level
in the mixture for the test organisms. Ten fish or clams were trans-
ferred from the acclimation tank into each test tank. Mortality in each
tank was checked at least every 12 hours over a 48-hour period. For
each sediment station, at least two complete series of experiments were
conducted. Criteria for death of mummichogs and spot were cessation
of opercular movement and no response to poking. The death of soft-
shell clams was indicated by open shells or no sign of closing shells when
poked or resisting the pressure of opening shells with fingernails.
E-13
-------
In the beginning and at the end of the 48-hour experiment, dissolved
oxygen, pH, temperature, salinity, suspended solids, dissolved solids,
total solids, and turbidity of the test sediment-water mixture in each
tank were determined. Dissolved oxygen, pH, temperature, salinity
and turbidity were determined by meters. Suspended solids and dissolved
solids were determined by standard methods (American Public Health
Association, 1971). Water quality and mortality data of the test organ-
isms in this study are presented in Tables E-] 0 through E-37, located
at the back of this appendix.
E. 4 RESULTS
E.4.1 Pollutants in Bioassay Sediment /Samples
For each of the nine bioassay stations, the Harbor sediment samples were
analyzed for moisture, hexane extracts, and heavy metal concentrations
(bulk analyses). Their averages, standard deviations, and coefficients
of variation were calculated (Table E-2). There was a wide variation among
the stations in the contents of these chemicals. Moisture was highest at
Station 8 and followed in decreasing order by Stations 9, 5, 2, 4, 1, 6,
and 10. Compared to the other parameters, moisture was least variable
from one station to another. The quantity of soluble material extracted
by hexane was highest at Station 5 followed in decreasing order by
Stations 2, 4, 1, 10, 8, 6, 9, and 7. PCB concentration was also highest
E-14
-------
TABLE E-2
Station
No.
1
2
3/4
5
6
7
8
9
10
Moisture
%
67.65
87. 33
75. 62
90.47
65.31
66.59
95; 21
94.46
58.90
Average Dl
77. 95
Standard Deviatio
14. 05
Coefficient of Var
18.02
MOISTURE, HEXANE EXTRACTS, PCB's AND HEAVY METAL CONTENTS
(BULK ANALYSES) DETERMINED FOR BALTIMORE HARBOR SEDIMENT
SAMPLES USED IN BIOASSAY, AND MUMMICHOG 24 HR-TLm VALUES
FOR SUSPENDED SOLIDS
Hexane
Extracts
mg/Kg
.9, 600
17, 600
10, 600
21,500
2,900
2, 300
3, 500
2, 500
6, 500
8,555.55
n (d)
7, 001.81
iation 1—
X
81.84
PCB's
mg/Kg
-
1,26
0.84
2. 10
0. 10
<0. 05
0. 16
0.41
0.21
0.64
0.53
100)
82.8
Metals, mg/Kg
As
229
75
53
71
13
44
29
42
31
65.22
64.52
98.93
Hg
2. 65
2.78
0.85
1. 15
0.45
0.47
0.32
0.27
0. 53
1. 05
0.98
\
90.48
Cd
7
15
43
45
2
2
2
2
4
13.55
17.77
131.14
* Sediment sample taken from the cores at the depth of 5
Cr
1, 810
1,460
470
4., 300
200
490
490
160
190
1, 063. 33
1, 347.42
126.72
cm.
Cu
580
1,830
2, 300
580
150
200
140
140
65
665.00
824.43
125.87
Mn
320
510
570
560
710
680
650
1, 500
180
631. 11
363.73
57.63
Ni
79
190
63
93
81
82
60
56
62
85. 11
41. 28
45.50
Pb
510
620
460
800
340
310
120
81
170
379. 00
241.06
63. 60
Zn
1, 010
1,400
430
5, 500
1, 070
1, 080
470
330
680
1, 385. 55
1,577.99
113.89
Mummichog
24 Hr-TLm
Values
11. 79
4,,93
4.65
0. 63
25.96
79.08
24. 64
-
8.44
20.22
25. 60
127.87
-------
at Station 5 followed in decreasing order by Stations 2, 4, 9, 10, 8, 6,
and 7. Of the heavy metals, Zn had the highest average concentration
followed in decreasing order by Cr, Cu, Mn, Pb, As, Ni, Cd, and
Hg. Coefficients of variation indicate that Cd, Cr, Cu, Zn, As, Hg,
and PCB concentrations were more variable among the stations than
Pb, Mn and Ni. The highest concentrations for any station were Cd, Cr,
Zn, Pb, and PCB at Station 5; As, Hg, and Ni at Station 1; Cu at Station 4
and Mn at Station 6. It was clear from the analyses that the sediment at
Station 5 was the most contaminated, and material from Station 7 was
probably the least contaminated.
Correlation analyses were conducted to determine the relationships
between chemical parameters determined for the nine stations
(Table E-3). Hexane extracts, PCB,Pb, Cr, Zn, and Cd were significantly
and positively correlated. A significant positive correlation was also
found between Hg and Pb, Ni and As, and Cr and Cu, but the correlation
coefficients were low. In contrast, Mn had a statistically insignificant
negative correlation with hexane extracts, PCB and all heavy metals: it
correlated with moisture positively, still at an insignificant level.
Moisture was independent from all parameters studied. Because hexane
mostly extracts non-polar organic materials from sediments, PCB and
heavy metals which show a high degree of correlation with the hexane
E-16
-------
TABLE E-3
CORRELATIONS AMONG HEAVY METAL CONTENTS, HEXANE EXTRACTS, PCB's,
MOISTURE, AND MUMMICHOG 24 HR-TLm VALUES FOR BALTIMORE HARBOR
SEDIMENTS STUDIED AT NINE STATIONS
1 2 3 4 5 6 7 8 9 10 11 12 13
1. Hexane Extracts
2. PCB's 0.96*
3. Pb 0. 90* 0. 88*
4. Cr 0.84* 0.91* 0.84*
5. Zn 0.77* 0.83* 0.78* 0.93*
6. Cd 0.76* 0.82* 0.72* 0.64 0.69*
7. Hg 0.63 0.62 0.66* 0.45 0.17 0.18
8. Ni 0.60 0.47 0.58 0.32 0.22 0.12 0.72*
9. Cu 0.55 0.47 0.53 0.13 0.07 0.66* 0.50 0.48
10. As 0.31 0.75 0.41 0.40 0.09 0.07 0.77* 0, 14 0.15
11. Mn -0.37 -0.15 -0.39 -0.25 -0.17 -0.18 -0.43 -0.21 -01.9 -0.33
12. Moisture 0.29 0.45 0.07 0.31 0.25 0.23 0,00 0.17 0.13 -0.13 0.56
13. Mummichog -0.65 -0.60 -0,42 -0.39 -0.21 -Q. 52 -0,41 -0.18 -0.43 -0.22 0.46 -0.29
24 Hr-TLm
Significant at 5% level (P 0. 05).
-------
extracts such as Pb, Cr, Zn, and Cd might relate with occurrence of this
organic fraction of the sediments. Moisture was least variable among
stations and -was independent from heavy metals and hexane extracts.
It seems that moisture has no relationship -with heavy metal concentra-
tions in the Harbor sediments. In other words, the dissolved form of
metals in the interstitial water of the sediments is perhaps so low com-
pared to the particulate form in the sediments that the sediment moisture
(interstitial water) is not a factor affecting bulk concentration of heavy
metals in the sediments.
E.4.2 Properties of Bioassay Sediment-Water Mixtures
It is known that sediments in the scoured deposited condition can have
high biological oxygen demands from deposited nutrients (Morton, 1976;
Saila, et al, 1972) and high chemical oxygen demands from various iron
sulfides and other chemicals (Slotta, 1974). When the sediments have
been exposed to oxygenated water, the sediment oxygen demands have
been known to increase eight to seventeen fold (Isaac, .1965; Reynolds,
et al, 1973). In order to maintain an adequate dissolved oxygen level in
the sediment-v/ater mixture for the test organisms, the Harbor sediment-
water mixtures in this study were stirred and aerated continuously for
at least 24 hours prior to and during the experiments. As a result of
the stirring and aerating processes, iron sulfides were changed to iron
E-18
-------
oxides and oxidized sulfur compounds (Slotta, 1974). The oxidation of
sulfides increased the mobility of metals such as silver, lead and zinc
from the sediments (Thomson, et al, 1973; Gordon, et al, 1972). The
pH values of the mixture decreased as the results of organic oxidation
and production of oxidized sulfur compounds. Therefore, the properties
of the sediment -water mixture in the bioassay were different from those
of the undisturbed deposited sediments.
Dissolved oxygen concentrations in the Harbor sediment-water mixture
and fuller's earth-water mixture in the bioassay remained consistently
above 5 mg/1, except in a few cases when the concentrations were slightly
lower (Tables E-10 - E-37). Turbidity, suspended solids, dissolved solids,
and pH varied 'according to sediment concentrations and among different
stations. In order to compare these parameters between experiments
with fuller's earth and the Harbor sediments, and also among the stations,
the relationships between suspended solids and the other two parameters,
turbidity, and pH, were considered.
The relationship between turbidity and suspended solid concentrations for
fuller's earth is different from those observed for the Harbor sediment-
water mixtures (Figure E-Z). It is evident that the turbidity produced by
a unit weight of suspended solids is much lower for fuller's earth-water
E-19
-------
100
err
«T
IS
"o
W>
TJ
0)
T3
C
0
a
(A
10
0.1
100
I
L
1000 10000
Turbidity, J.T.U.
I
100000
Figure E-2 Relationship between turbidity and suspended solid concentrations
for fuller's earth-water mixture (F) and Baltimore Harbor
sediment-water mixture (Stations 1-10).
E-20
-------
mixture than that for Harbor sediment-water mixture. The difference
among Harbor samples suggests that physical properties of suspended
solids may differ between fuller's earth and the Harbor sediments, and
among the sediments at the nine stations.
The relationship between pH values and suspended solid concentrations
is shown in Figure E-3. For fuller's earth-water mixture, the pH value
decreased very slightly as suspended solid concentration increased.
The mixture always remained basic and its pH remained at 7. 2 or higher.
For the Harbor sediment-water mixture, the pH value decreased very
rapidly as suspended solid concentration increased and reached the
minimum at a concentration of about 20-30 g/1 suspended solids for all
stations. This fact might suggest that a factor related to suspended
solids controlled the change of chemical equilibrium in the mixture, and
this change was stabilized at this suspended solid concentration. If the
release of toxic chemicals from the sediments into the mixture was
involved in this chemical equilibrium, the dissociation of toxic chemicals
from the sediments may have reached a maximum level at approximately
20-30 g/1. The concentration of suspended solids may, therefore, be
one of the important factors controlling the release of toxic chemicals
in the sediment-water mixture. There were differences in the rate of
pH reduction and in the pH minimum among the stations. The stations
E-21
-------
ro
IS)
120 140
Suspended Solids, 9/j
Figure E-3 Relationship between suspended solid concentrations and pH values for fuller's earth-water
mixture (F) and sediment-water mixture of Baltimore Harbor (Stations 1-10, except 9).
-------
which had the faster rates in pH reduction had the lower pH minima.
The fastest rate in the pH reduction and the lowest value in pH minimum
were at Station 5 (pH minimum about 3. 5) followed in order by Stations
2, 4, 1, 8, 10, 6, and 7 (pH minimum about 4. 7). The differences may
be due to the difference in quality and/or quantity of chemicals, including
toxic substances, released from the sediments.
The exception was Station 9. The sediment-water mixture was basic;
and the pH values ranged between 8. 9 to 9. 3, higher than those of control
water and of fuller's earth-water mixture (Table E-15). This is
notably different from the other sediment water mixtures. The reason
for the high pH values of Station 9 was not known. The sediment of this
station was black like those from other stations, but contained many white
clay-like lumps ranging in size from a millimeter to about 7. 5 centimeters
When the sediment-water mixture was made, these lumps were broken
into pieces and mixed well with the sediments. According to personal
communication with Dr. Raymond Morgan, Chesapeake Biological Labor-
atory, these lumps may have been a kind of paint binder. It was suspected
that these clay-like lumps might strongly affect the sediment-water mix-
ture properties.
E-23
-------
E.4.3 Time-Concentration Relationship
Median survival time is the length of the period between the time when
the organisms are: initially exposed to a test solution and the time when
50 percent mortality of the test population has occurred. This time was
calculated from the equation describing the relationship between exposure
time and probits (Finney, 1971) of cumulative mortality for each species
at each concentration (Bliss, 1937). Then the relationships between
median survival time and suspended solid concentrations were plotted
for each species for fuller's earth and for the Harbor sediments at
each station (Figure E-4). Generally, the median survival time increased
as suspended solid concentration decreased, but the rate of the increase
differed among the three species tested.
For spot, the rate of increase in median survival time as suspended solid
concentration decreased was so fast that at all stations the median sur-
vival time approached infinity after 1440 minutes or 24 hours (Figure E-4).
This suggests that spot will be able to survive indefinitely in the sediment-
water mixture if they can survive for 24 hours. For mummichogs, the
increase in the median survival time as suspended solid decreased was
slower than that of spot (Figure E-5). It appears that most of the mummi-
chogs will be able to survive indefinitely in the sediment-water mixture
E-24
-------
c
8
>
*>
2*
c
8
H
5.000
500
1
0.5
10
50 TOO
Suspended Solids,g/l
Figure E-4 Relationship between suspended solid concentrations and median survival time for spot
exposed to fuller's earth-water mixture (F) and the sediment-water mixture of Baltimore
Harbor (Stations 1-10).
-------
H
t
DO
5 1
Suspended Solids, g/l
Figure E-5 Relationship between suspended solid concentration and median survival time for mummichogs
exposed to fuller's earth-water mixture (F) and the sediment-water mixture of Baltimore
Harbor (Stations 1-10).
-------
if they can survive for 24 hours. Some of them will die after 24 hours.
For soft-shell clams, the median survival time increased very slowly as
suspended solid concentration decreased, a relationship very different
from that for the two fish species tested (Figure E-6).
On the basis of median survival time, Station 5 was most toxic for all
species, followed in decreasing order with small variations by Stations
2, 4, 10, 1, 8, 6, and 7. The fuller's earth-water mixture was dis-
tinctly less toxic than any sediment-water mixture from Baltimore Harbor.
E.4.4 Mortality-Concent rat ion Relationship
The data on water quality and mortality of the three species of test
organisms obtained in the bioassay are listed in Tables E-10 - E-37.
For mummichogs and spot, the 24-hour and 48-hour percent mortality
was transferred into probits and their relationship with suspended solid
concentrations was established for each station. On the basis of the
relationship equations, their 24-hour and 48-hour TLm values (median
tolerant levels, the concentrations at which 50 percent of a test popula-
tion was killed by the exposure for 24 hours and 48 hours respectively)
for suspended solids were calculated for fuller's earth-water mixture
and for the Harbor sediment-water mixture at eight stations. Because
E-27
-------
500
0)
£
• ••
I-
"o
>
*>
k.
3
c
0
• if*
•3
100
50
10
aKggC*5*Sg;
Suspended SoJsds,
Figure E- 6 Relationship bet-ween suspended solid concentration and median survival
time for soft-shell clams exposed to fuller's earth-water mixture (F)
and the sediment-water mixture of Baltimore Harbor (Stations 1-10).
E-28
-------
of limitations in the capacity of the aerating and stirring systems and
the high tolerance of the soft-shell clams to the sediments, it was
impossible to make a sediment-water mixture concentrated enough to
obtain 24-hour and 48-hour TLm for the clams in fuller's earth-water
mixture and the Harbor sediment-water mixture at Stations 6, 7, and 8.
Therefore, a 96-hour bioassay was conducted for them. The TLm values
obtained for the soft-shell clams in this study were for exposure times of
24 hours and 48 hours for Stations 1, 2, 4, 5, and 10; 48 hours and 72
hours for Station 8; and 72 hours and 96 hours for Stations 6 and 7 and
fuller's earth. The TLm values for suspended solids obtained for the
three species of test organisms are shown in Table E-4.
When 24 hour TLm values and 48-hour TLm values for suspended solids
were compared for each of the three species at each Harbor sediment
station, it was found that there was a very strong positive correlation
(r = 0. 99) between the two values (Figure E-7). The results of analyses of
convariance indicated that the slope of the regression line for soft-shell
clams is similar to that of spot (P> 0.20), about 1, but different from
that of mummichogs (P> 0. 005). The elevation of the regression line for
soft-shell clams is substantially different from that of both spot and mum-
michogs (P > 0. 005). It is evident that the 24-hour TLm and 48-hour TLm
increased proportionally for the three species of test organisms. In
E-29
-------
M
TABLE E-4
TLm VALUES (SUSPENDED SOLIDS, 81e) FOR MUMMICHOGS, SPOT
AND SOFT-SHELL CLAMS EXPOSED TO BALTIMORE HARBOR SEDIMENT-WATER
AND FULLER'S EARTH-WATER MIXTURE
Station
No.
1
2
4
5
6
7
8
10
fuller1 s
earth
* Values
Mummichogs
24
11
4
4
0
25
79
24
8
107
hr.
.79
.93
.65
.63
.96
.08
.64
.44
.48
48
9
4
3
0
22
66
20
7
103
hr.
.72
.21*
.74
.58*
.96
.78
.59
.23
.29
calculated from the formula
24
9
5
6
0
24
31
18
8
Spot
hr.
.36
.78
.05
.74
.99
.89
.89
.44
50. 61
in Figure
48
9
5
5
0
24
29
18
8
50
4-
Soft-- Shell Clams
hr. 24 hr. 48 hr. 72 hr. 96 hr.
.31 160.98 136.82
.22 53.65 16.96
.86* 84.56 57.88
.60 33.30
.92 - - 149.94
.12 - - 120.28 96.94
.04 - 111.08 93.99
.40 156.76 125.50
.61 - - 188.58 137.20
6.
-------
150
o
v»
V)
"U
*M
"o
U)
C
O
Q.
V)
3
100
0
E
50
0
50
100
150
24 hr-Ylm Values (Suspended Soiids,
Figure E-7 Relationship between 24-hour TLm and 48-hour TLm values of mummichogs
(solid circles; Y = 0. 043 + 0. 82 X, n = 7, r = 0. 99), spot (open circles;
Y = -0. 0058 + 0. 98 X, n = 7, r - 0. 99), and soft-shell clams (stars;
Y = -36. 72 + 1. 06 X, n = 4, r = 0. 99) for suspended solids of Baltimore
Harbor sediments.
E-31
-------
other words, the two values are mutually convertible for the three species
when exposed to Harbor sediments. The results also suggest that for
soft-shell clams the 24-hour TLm values are, on the average, about
37 g/1 higher than 48-hour TLm values. For spot there is no significant
difference between 24-hour TLm values and 48-hour TLm values. For
mummichogs 24-hour TLm values increased at a slightly faster rate
than 48-hour TLm values. There is, therefore, species specificity in
mortality response to the Harbor sediment-water mixture.
For comparison of sediment susceptibility among spot, mummichogs,
and soft-shell clams, 24-hour TLm values of mummichogs were plotted
on the abscissa and the 24-hour TLm values of the three species were
plotted respectively on the ordinate in Figure E-8. The mummichogs1 rela-
tion line is a straight line passing through the origin of the graph at
45 degrees. The spot relation line is curvilinear, and it departs from
the mummichogs' line at Stations 6, 8, and 7. The soft-shell clams' line
is also curvilinear, but it bends to the opposite direction of that for the
spot at the low TLm values of Station 5 and especially at the high TLm
values of Stations 6 and 8. It is evident that spot are more susceptible
than mummichogs to fuller's earth and Harbor sediments at Station 7,
for which the TLm values are high; whereas both species of fish have
similar susceptibility to the Harbor sediments at Stations 1, 2, 3, 4,
E-32
-------
100
50
o
73
toi
•8 10
C
0)
&
VI
3 5
li
0.5
0.5
5 10
24 hr-TLm (Suspended
Mummichog
50 100
Solids,g/l)
Figure E-8 Comparison of 24-hour TLm values among mummichogs (solid circles),
spot (open circles), and soft-shell clams (stars) for fuller's earth (F)
and Baltimore Harbor sediments (Stations 1-10).
E-33
-------
5, 6, 8, and 10 where TLm values are low. On the basis of the 24-
hour TLm values, the susceptibility of spot to fuller's earth and to the
sediments at Station 7 was 42 percent and 48 percent, respectively,
more than those of mummichogs. It appears that spot are more suscep-
tible than mummichogs to suspended solids, but both species have similar
susceptibility to toxic materials released from Harbor sediments. For
soft-shell clams, the Harbor sediments at Stations 1, 2, 4, 5, and 10
were toxic enough to produce 50 percent mortality within 24 hours.
The sediment susceptibility of the clams was much less than that of
mummichogs, ranging between 53 times less at Station 5 and 13 times
less at Station 2. At Station 6, 7, and 8 and for fuller's earth, soft-shell
clams were so tolerant to the suspended solids that there was little or
no mortality in 24 hours. Accordingly, as compared to spot and mummi-
chogs, soft-shell clams were very tolerant to toxic materials and even
more tolerant to suspended solids contained the Harbor sediments.
Soft-shell clams can contract to reduce the surface area exposed to toxicants
or reduce the rate of pumping water through their gills as parts of their
defense mechanisms in an extremely unfavorable environment. This may
have been the case in the highly toxic solution of Station 5 sediment and
in the highly concentrated suspended solid mixtures of fuller's earth and
of Stations 5, 8, and 7 sediments so that their survival time increased
and the mortality rate was reduced.
E-34
-------
It is interesting to note that the relation lines for spot and soft-shell
clams increase their curvature and deviate farther from the mummichog
relation line at about 20 g/1 suspended solids (Figure E-8). This concen-
tration coincides approximately to that of the sediment-water mixture
at which pH values approach the minimum (Figure E-3). This evidence
further supports the possibility that the amount of toxicants released
from the Harbor sediments into the mixture was proportional to the sus-
pended solid concentration until the mixture reached about 20 g/1 of
suspended solids. At approximately this concentration, the chemical
dissociation and content of toxic chemicals in the mixture may reach the
maximum. With further increase in the sediments in the mixture, the
toxic constituents of chemicals in the mixture might remain fairly constant,
while the suspended solid concentration increases and becomes a more
important factor for fish mortality.
E-35
-------
E. 5 DISCUSSION
E. 5. 1 Gross Toxicity of Baltimore Harbor Sediments
Because the 24-hour TLm values and 48-hour TLm values were mutually
convertible and there was no important difference in the order of sedi-
ment susceptibility among the three species at eight stations, the mum-
michog 24-hour TLm value for suspended solids in this study was selected
as the index of gross toxicity for Baltimore Harbor sediments. On the
basis of this index, Station 5 was most toxic, followed in decreasing
order by Stations 4, 2, 10, 1, 8, and 6; and Station 7 was the least toxic.
This is the same order found in the study of the time-concentration
relationship. The difference in gross toxicity between the two extreme
cases at Station 5 and Station 7 was about 125 times ^n terms of 24-hour
TLm. It is evident that a wide range exists in the gross toxicity of
Harbor sediments among different locations. The fuller's earth-water
mixture was about 18 percent less toxic than the sediment-water mixture
from Station 7.
In 1970-1971, the Center for Environmental and Estuarine Studies (1974)
conducted a comprehensive biological study of Baltimore Harbor, including
benthic invertebrates, crabs, fish eggs and larvae, and adult fish. In.
the study of benthic invertebrates, 28 sampling stations were designed,
E-36
-------
and at each station four samples were collected with a van Veen grab
in March, June, September, and December of 1970. In this study; the
species diversity index of each sample was calculated using Margalef's
S- 1
formula, d = , where S is the number of species and N is the total
Log N
number of individuals (McErlean and Mihursky, 1968). The average
index was obtained from the four samples for each station. Of these
stations, Station 17 (18), 15, 3, 26, 23, 7, and 20 were either almost
identical or near to the sediment stations 2, 4, 5, 6, 7, 8, and 10 of
this study. When mummichog 24-hour TLm values for suspended solids
were plotted against average species diversity indexes of the seven stations,
it was found that there is a somewhat sigmoid relationship between the two
values (Figure E-9). When Station 7 and Station 5, with exceptionally high
and low toxicity, are not included in consideration, there is a generally
linear relationship for the remaining five stations. According to this
straight line relation formula in Figure E-9, the average species diversity
indexes at 28 stations for benthic invertebrates could be converted into
mummichog 24-hour TLm values for suspended solids. Using these
mummichog 24-hour TLm values as the indexes of gross toxicity, the
distribution of the sediment gross toxicity in Baltimore Harbor could
be mapped on the basis of arbitrary limits (Figure E-10). According to
the sediment gross toxicity, the Harbor sediment can be divided into
four toxic zones: a highly toxic zone where mummichog 24-hour TLm
E-37
-------
5.0
X
£
x
4-
• KB
0)
5
.2
o
Q.
i.o
0.5
6
1.0
5.0 10
SO
24-hr Tim (Suspended Solids,
Figure E-9 Relationship between mummichog 24-hour TLm values for suspended
solids and species diversity indexes of benthic invertebrates at seven
stations in Baltimore Harbor. The regression equation of solid line
is Log10Y = -0.5678 + 0.4782 Log10X (n = 5, r-0.89).
E-38
-------
TOXIC ZONE
//
*4>
Figure E-10 Distribution of toxic zones and mummichog 24-hour TLrn values for
suspended solids in Baltimore Harbor (numbers in squares, real values
obtained from the bioassay; numbers not in square obtained from con-
version of species diversity indexes of benthic invertebrates).
E-39
-------
values are less than 8 g/1 suspended solids; a moderately toxic zone
where the TLm values are between 8 g/1 and 20 g/1; a low toxic zone
where the TLm values are between 20 g/1 and 40 g/1, and a slightly
toxic zone where the TLm values are higher than 40 g/1. This zoning,
with obvious imprecision, provides a useful display of the areas with
greatest degradation and permits an estimation of the area of sediment
which must be considered in efforts to correct or improve sediments of
various toxicities in Baltimore Harbor (Figure E-10).
E. 5.2 Relationship Between Biota and Sediment Toxicity
in Baltimore Harbor
Thirty species of benthic invertebrates belonging to six phyla were
found in Baltimore Harbor in the 1970 study by the Center for Environ-
mental and Estuarine Studies (1975). The distribution of species diversity
indexes at 28 stations in. the Harbor is shown in Figure E-ll. The index
decreased from the slightly toxic zone to the highly toxic zone and was
related to the distribution of sediment toxicity as noted in establishing
the zones. Of the six phyla, Arthropoda, Mollusca, and Annelida were
dominant groups of benthic invertebrates in the Harbor. They were
almost equal in number of species in the slightly toxic zone. The number
of species in Mollusca and Arthropoda, particularly the latter, decreased
at the stations where sediment toxicity increased. In the highly toxic
E-40
-------
SPECIES DIVERSITY INDEX
>1.50
Figure E- 11 Distribution of species diversity indexes for benthic macro-invertebrate
community in Baltimore Harbor (based on data from H. T. Pfitzenmeyer,
Center for Environmental and Estuarine Studies, 1975).
E-41
-------
zone, they were either absent or nearly absent, while Annelida became
a dominant group in the zone (Figure E-12). It is evident that Mollusca and
Arthropoda are more sensitive than Annelida to the sediment toxicity.
The other three phyla -- Coelenterata, Nemertea, and Insecta -- were
rare in the Harbor and limited in the sediments mostly in the low and
slightly toxic zones. Relative abundance of the species in the six phyla
in the four toxic zones is shown in Table E-5. Most species decreased in
abundance from the slightly toxic zone to the highly toxic zone, except
some species of Annelida: Limnodrilus sp. , Heteromastus filiformis,
Scolecolepides viridis, and Streblospio benedicti, which increased in
abundance in the low and/or moderately toxic zones.
The relative abundance of blue crabs at the 12 stations studied in 1970
(Center for Environmental and Estuarine Studies, 1975) is shown in
Figure E-13. They were abundant at the mouth of the Harbor and tended
to decrease toward the Inner Harbor. As the crabs are semi-benthic
organisms, according to Lippson and Miller (Center for Environmental
and Estuarine Studies, 1975), their abundance seems not to relate to the
sediment toxicity alone, but also to the physical type of the bottom.
They were abundant at the stations where bottoms were composed of mud
and rocks and were rare at the stations where the bottoms were covered
with oil and grease-like substance.
E-42
-------
Annelida
o
Arthropoda
Mollusca
Others
Figure E-12 Percentage species composition of three phyla, Annelida, Arthropoda,
and Mollusca in Baltimore Harbor (Based on data from H. T. Pfitzen-
meyer, Center for Environmental and Estuarine Studies, 1975).
E-43
-------
TABLE E-5
RELATIVE ABUNDANCE OF BENTHIC INVERTEBRATES
IN THE TOXIC ZONES OF BALTIMORE HARBOR, 1970
(Based on data from H. T. Pfitzenmeyer in Center
for Environmental and Estuarine Studies, 1975)
Phylum
Coelenterata
Nemertea
Annelida
Arthropeda
Insecta
Mollusc a
Species
Fagesia lineata
Diadumene leucolena
Micrura leidyi
Limnodrilus sp.
Heteromastus filiformis
Scolecolepides viridis
Streldospio benedicti
Eteone heteropoda
Nereis succinea
Hypaniola grayi
Polydora ligni
Balanus amphitrite
Neomysis americana
Cyathura polita
Edotea triloba
Monoculodes edwardsi
Janimarus sp.
Carinogammarus mucronatus
Melita nitida
Cymadusa compta
Leptochierus plumulosus
Corophium lacustre
Rithropanopeus harrisi
Chironomus atlenuatus
Procladius sp.
Brachiodonte recurvus
Congeria leucophaeta
Macoma balthica
Macoma phenax
Rangia cuneata
Toxic Zones
Slightly
++
+ +
!r
L
+
+++
Low
+
++
H;:
i
-
Moderately
+
;r
+
+
r+
Highly
T
-
*
++++ Very Abundant
+++ Abundant
""""" Common
+ Rare
Absent or nearly absent
E-44
-------
NUMBER OF CRABS COLLECTED
>75
Figure E-1 3 Number of blue crabs collected in seven samples at 1Z stations in
Baltimore Harbor (Data from R. L. Lippson and R. W. Miller,
Center for Environmental and Estuarine Studies, 1975).
E-45
-------
Fish are free moving organisms, and their habitats change through
their life history. Their occurrence and abundance in the Harbor are
influenced strongly by tidal cycles, weather, seasons, water quality,
food availability, fish behavior, and stages of life history. Food avail-
ability and water quality are often influenced by sediment toxicity.
Therefore, the species diversity and abundance of the fish in the Harbor
may be affected by the degree of sediment toxicity. In the 1970 study,
fish were sampled by three methods: 50-foot shore seine with 1/2-inch
mesh, 25-foot semi-balloon otter trawl with 1/2-inch mesh, and one-
meter plankton net with mesh opening of 0. 4 by 0. 6 mm. In this study
the fish data were rearranged in order to find the relationship between
fish and s'ediment toxicity. The distribution of species diversity sampled
by the three methods is shown in Figures E-14 - E-16. Their relative abun-
dance is shown in Tables E-6 - E-8. For the fish sampled by shore seine and
trawl, there was a trend of reduction in species diversity index from the
slightly toxic zone to the highly toxic zone, but the trend was not so
obvious as that of the benthic invertebrates. For the fish sampled by
the plankton net in the Harbor channel, the species diversity index appears
to be little related to the sediment toxicity. For the fish collected by
the three methods, relative abundance of most species tended to decrease
as sediment toxicity increased (Table E-6). Exceptions were silversides
in water near the shores and white perch, rock fish, and alewife in the
E-46
-------
SPECIES DIVERSITY INDEX
>0.70
Figure E-14 Distribution of species diversity indexes of fish sampled by a 50-foot
shore seine in Baltimore Harbor (based on data from M. L. Wiley,
Center for Environmental and Estuarine Studies, 1975).
E-47
-------
SPECIES DIVERSITY INDEX
> 0.80
Figure E- 1 5 Distribution of species diversity indexes of fish sampled by a 25-foot
semi-balloon otter trawl in Baltimore Harbor (based on data from
W. L. Wiley, Center for Environmental and Estuarine Studies, 1975).
TO-48
-------
SPECIES DIVERSITY INDEX
Figure E- 1 6 Distribution of species diversity indexes of fish sampled by a. one-meter
plankton net in Baltimore Harbor (based on data from M. L. Wiley,
Center for Environmental and Estuarine Studies, 1975).
E-49
-------
TABLE E-6
RELATIVE ABUNDANCE OF SHORE FISH
IN THE POLLUTED ZONES OF BALTIMORE HARBOR
(Based on data from M. L. Wiley, Center for
Environmental and Estuarine Studies, 1975)
Species
Toxic Zones
Slightly Low Moderately
Highly
Menidia menidia +++
Morone americana +++
Fundulus heteroclitus +++
Cyprinus carpio ++
Fundulus diaphanus ++
Alosa aestivalis +
Alosa pseudoharengus +
Morone saxatilis +
Dorosoma cepidianum +
Lepomis gibbosus +
Fundulus majalis +
Anchoa mitchilli +
Hyporhamphus unifasciatus +
Menidia berglina +
Perca flavescens +
Ictalurus catus +
Anguilla rostrata +
-t-
++
++++ Very abundant
+++ Abundant
+ + Common
+ Rare
Absent or nearly absent
E-50
-------
TABLE E-7
RELATIVE ABUNDANCE OF FISH COLLECTED BY A
12-FOOT SEMI-BALLOON OTTER TRAWL WITH A
1/2-INCH STRETCH MESH IN THE POLLUTED ZONES
OF BALTIMORE HARBOR, APRIL TO DECEMBER 1970
(Based on data from M. L. Wiley, Center for
Environmental and Estuarine Studies, 1975)
Species
Toxic Zones
Low
Moderately
Highly
Morone americana
Morone saxatilis
Alosa pseudoharngus
Anchoa mitchilli
Ictalurus catus
Lepomis gibbosus
Perca flavescens
Alosa aestivalis
Anguilla rostrata
Menidia sp.
Trinectes maculatis
Pomatomus saltatrix
Cyanoscion regalis
Leiostomus xanthurus
Opsanus tau
Fundulus heteroclitus
-H+
++++ Very abundant
+++ Abundant
++ Common
+ Rare
Absent or nearly absent
E-51
-------
TABLE E-8
RELATIVE ABUNDANCE OF FISH EGGS, FISH LARVA, AND
JUVENILE FISH COLLECTED WITH 1-METER PLANKTON NET
IN THE TOXIC ZONES OF BALTIMORE HARBOR, 1970
(Based on data from M. L. Wiley in Center for
Environmental and Estuarine Studies, 1975)
Species
Toxic Zones
Slightly
Low Moderately
Highly
LARVA AND JUVENILES
Alosa sp.
Anchoa mitchilli
Menidia sp.
Gobiosoma bosii
Morone americanus
Dorosoma cepediunum
Lepomis gibbosus
Brevoortia tyrannus
Fundulus sp.
Notropis hudsonius
Chasmodes bosquianus
Anchoa mitchilli
Trinectus maculatus
EGGS
+++ Abundant
++ Common
+ Rare
Absent c?r nearly absent
E-52
-------
off-shore water. These fish were abundant in all zones and their distri-
bution appears to be unrelated to sediment toxicity. Some bottom dwelling
or bottom feeding species, such as winter flounders, Atlantic croaker,
and hogchoker were absent in the Harbor.
The use of Baltimore Harbor as a spawning ground of fish was very
limited. Only the eggs of Bay anchovy were found in both slightly and
low toxic zones during the late spring and summer. The eggs of the hog-
choker were found only in the Outer Harbor of the slightly toxic zone in
July.
Bowman (1974) made biweekly samplings of phytoplankton at seven
stations in Baltimore Harbor and two stations in Chesapeake Bay in the
vicinity of the entrance to the Harbor. A total of 68 genera was found.
The distribution of diversity indexes of genera calculated from Margalef's
formula is shown in Figure E-17, and relative abundance of each genus is
shown in Table E-9. The difference in genus diversity indexes was small.
between 0. 51 and 0. 71 at the Harbor stations, lower than 0. 85 at the
Bay stations. The stations in higher toxic zones tended to have slightly
lower diversity than those in less toxic zones. The-total number of
genera which occurred from March to August 1971 was 39 in the slightly
toxic zone and low toxic zone, 52 in the moderately toxic zone, and
E-53
-------
DIVERSITY INDEX
>0.7
>0.6
>0.5
Figure E-17 Distribution of genus diversity indexes of phytoplankton in Baltimore
Harbor (based on data from G. A. Brown, 1974).
E-54
-------
TABLE E-9
RELATIVE ABUNDANCE OF PHYTOPLANKTON
IN VARIOUS TOXIC ZONES OF BALTIMORE HARBOR,
MARCH-AUGUST, 1971
(Based on data from G. A. Brown, 1974)
_ Toxic Zone
Genus
Slightly Low Moderately Highly
Skeletonema
Scenedesmus
Pediastrum
Exuviella
Chlamydomonas
Dictyosphaerium
Goniaulax
Oscillatoria
Ulothrix
Anabaena
Prorocentrum
Aphanizomenon
Ankistrodesmus
Coelastrum
Oocystis
Tetrustrum
Coscinodiscus
Fragilaria
Melosira
Nitzschia
Chaetoceros
Navicula
Synedra
Cyclotella
Asterionella
Peridinium
Gleocystis
Staurastrim
Amphiprora
Meridion
Continued.
E-55
-------
TABLE E-9 (Continued)
Genus
Toxic Zone
Slightly
Low Moderately Highly
Rhizosolenia
Cocconeis
Diatoma
Cymbella
Tabellaria
Cerataulina
Pleurosigma
Dinobryon
Tribonema
Thallasiosira
Microthamnion
Surirella
Microspora
Synura
Hormidium
Stigeoc Ionium
Ceratium
Crucigenia
Biddulphia
Amphora
Anacystis
Rhopalodia
Actinastrum
Diploneis
Anacystis
Botryococcus
Mallomonas
Kirchneiella
Phormidium
Stephanodiscus
Gymnodinium
Tetraedron
Eudorina
Eutreptia
Gleocapsa
+ + + + Very Abundant
+++ Abundant
++ Common
+ Rare
Absent or nearly absent
E-56
-------
49 in the highly toxic zone. The presence of a low diversity index by
occurrence of high numbers of genera suggests an unstable phytoplankton
community with the high turning over of genera at different times of the
year in the highly toxic zone. The phytoplankton community in the
Harbor was less diverse than that in the adjacent Chesapeake Bay,
indicating the stressed condition of phytoplankton in the Harbor.
Several genera, such as Coscinodiscus, Fragillaria, Melosira, Nitzchia,
Schnedesmus, and Pediastrum, were abundant in all zones. Exuviella,
Chlamydomonas, Pietyosphaerium and some other genera were common
only in the slightly toxic zone, while Navicula, Chaetoceros and Synedra
were commonly in the moderately and highly toxic zones.
E. 5. 3 Ecological Effects of In-Place Pollutants
in Baltimore Harbor
According to the wide variation in gross toxicity among the sediments
tested, the in-place pollutants in the Harbor sediments are clearly not
homogeneously distributed but fairly patchy in distribution, perhaps
because of their sources and local events. They seem not to be trans-
ported for long distances by water and Harbor activities. Except for
extreme storm conditions, they appear unlikely to be transported in
large quantities from the Inner Harbor to the Outer Harbor or from the
Harbor to the Bay. The Harbor sediments have become a sink or trap
E-57
-------
for much of the pollutants produced by domestic and industrial activities
of the City of Baltimore.
The present biotic structure and distribution in the Harbor resulted from
the combined effects of pollutants in the water column, derived directly
from the discharges of domestic and industrial wastes, and of pollutants
accumulated in the Harbor sediments. The benthic invertebrates and
bottom dwelling fish are in constant contact with the sediments and feed
primarily on foods produced in or on them. They have been the organisms
most seriously affected by toxic chemicals in the sediments. The pelagic
organisms are influenced primarily by toxic chemicals in the water column,
whose sources are direct domestic and industrial waste discharge, import
from the Bay, and, to some degree, release from the bottom sediments.
The transfer of contaminants such as heavy metals, nutrients and
pesticides across the sediment-water interface is complex and not yet
fully understood. Morton (1976) reviewed the literature and identified
several factors important to the process, such as sediment clay content,
organic fraction, redox potential, pH, bacteria, sulfur cycle and iron
cycle. The clay particles preferentially sorb heavier metallic ions
(Reynolds, et al, 1973). Metals which form highly insoluble metal sulfides
have little chance of leaving the sediments. Relatively soluble metal
E-58
-------
compounds might migrate up the sediment column until encountering an
aerobic environment which may set the limit of their mobility if they
are converted to insoluble oxide compounds. On the basis of solubility
product constants for the sulfide compounds of metals, Pb, Cd, Ni, Hg,
Ag, Cu, and Zn should remain essentially fixed in sediments having inter-
stitial water with a sulfide ion activity of 10~9 moles/liter. Mn and Fe
will be readily mobilized since MnS and FeS have high solubility
(Thomson, et al, 1973). Accordingly, even though there is some trans-
fer of contaminants from the sediments to the water column, the process
will be very slow and ecological effects on the water column might be minor.
Two likely pathways by -which toxicants enter the food chain in the water
column in the estuary are from the sediments into rooted plants and
ingestion of solid particles with sorbed toxicants by organisms (Wolfe,
1973). The in-place pollutants in Baltimore Harbor are indeed a problem,
particularly for bottom dwelling organisms, but they exist as a nearly
immobile reservoir. A different kind of biological threat is posed by
domestic and industrial wastes which have been and are discharged to
the Harbor not only to contaminate the Harbor water, but also to "enrich"
pollutants in the bottom sediments. The input of these is still substantial
(Maryland Environmental Service, 1974).
E-59
-------
The flushing rate of the open fairway has been found to be relatively
high (Stroupe, et al, 1961). It is suspected that if the domestic and
industrial waste discharges were suspended, water quality of the water
column in the Harbor would return to a nearly natural condition, and fish
and other pelagic organisms •would repopulate to form a healthy water
column community in a short period of time. It would take a longer
time for benthic communities to recover toward natural and healthy con-
ditions, and these might never be reestablished over the more seriously
polluted areas. If the in-place pollutants alone of the Harbor -were
cleaned up and domestic and industrial wastes were still .discharged into
the Harbor, water quality of the Harbor water column would remain con-
taminated as before; and pelagic biotic communities would remain unhealthy.
The toxicants from the wastes in the water column would continue to be
trapped by suspended solids and settle quickly to the bottom to form
additional toxic sediments. Accordingly, the present in-place pollutants
in Baltimore Harbor are of considerable concern, but they cannot be
fully corrected except through simultaneous treatment and the prevention
of further additions from domestic and industrial waste discharges.
Because of the presence of high concentrations of persistent pollutants,
particularly heavy metals, in Baltimore Harbor sediments, concern
exists about the possible danger of release of these pollutants into the
E-60
-------
water column and their concentration, cycling and magnification in the
food web, so-called bioconcentration. American oysters, Crassostea
virginica, are known to concentrate in ten weeks an amount as much as
50, 000 times the lead, zinc, copper; 700 times the cadmium and about
500 times the chromium in the surrounding water (Shuster and Pringle,
1969). Fish are known to accumulate mercury as much as 3, 000 times
that in the surrounding water (Johnels and Westermark, 1969; Hannerz,
1968).
i-
In the Upper Chesapeake Bay, this possible bioconcentration of heavy
metals in oysters resulting from spoil disposal of Baltimore Harbor sedi-
ments into the Kent Island and other open Bay spoil areas caused concern
in the late 1960's, and was studied in 1970 (Cronin. et al, 1974). The
results of the study indicated that the heavy metal concentrations in the
oysters were below "alert levels", and the uptake of metals by the oysters
had no detected relationship to the concentration of the metals in surround-
ing water or on suspended sediments. Also, the concentration of metals
in the oysters were, to a high probability, independent of distance from
the bottom. Instead, uptake rates were related to growth rate and
salinity or some factors coincident with it. It appears that the heavy
metal concentration in the water column and in the bottom sediments did
not cause a dangerous concentration in the oysters in the Chesapeake Bay
E-61
-------
and also were not factors at all in bioconcentration of the metals in
oysters. Morgan (1972) exposed clams, Macoma balthica, M. phenax,
and Rangia cuneata, in Baltimore Harbor water for eight weeks. It was
found that concentrations of the heavy metals in clams were very minor,
and in some instances there were no significant differences from those
in the control. Morton (1974) concluded from his literature review that
biological uptake and accumulation by aquatic organisms did not occur
as might be expected in polluted areas. This has caused a controversy
over the relative significance of bioconcentration. It is still impossible
to predict if and to what extent bioconcentration will occur, because the
potential release of toxicants across the sediment-water interface is
complex and not well understood.
E-62
-------
E. 6 SUMMARY
In-place pollutants in Baltimore Harbor are patchy in distribution.
Sediment from the most toxic station sampled was about 125 times as
potent as that from the least toxic. Among the pollutants determined,
hexane extracts correlated significantly with bulk concentrations of
PCB, Pb, Cr, Zn, and Cd, but the sediment moisture had no relation-
ship to heavy metal contents.
For the three species of estuarine organisms, spot, mummichogs, and
soft-shell clams, 24-hour TLm and 48-hour TLm values for suspended
solids correlated strongly and, thus, these two values for each species
were mutually convertible.
Spot -were more susceptible to suspended solids than mummichogs, but
both species had similar susceptibility to toxic chemicals released from
the Harbor sediments. As compared to these two fish species, soft-shell
clams were very tolerant to toxic materials and even more tolerant to
suspended solids.
Based on mummichog 24-hour TLm values for suspended solids used as
the index of sediment gross toxicity, the Baltimore Harbor sediments
E-63
-------
may be divided into four toxic zones: a highly toxic zone, with TLm
values less than 8 g/1; a moderately toxic zone, with TLm values between
8 g/1 and 20 g/1; a low toxic zone, with TLm values between 20 g/1 and
40 g/1; and a slightly toxic zone, with TLm values higher than 40 g/1.
The effects of sediment toxicity on benthic macro-invertebrates, fish,
and phytoplankton are evaluated. The community structure and diversity,
and distribution of benthic macro-invertebrates are related to sediment
toxicity and thus they are mainly affected by in-place pollutants in the
Harbor sediments. Pelagic fish and phytoplankton are mainly affected by
pollutants in the water column and very little, if present, by the in-place
pollutants in the sediments.
The ecological effects of in-place pollutants in Baltimore Harbor were
evaluated. These pollutants are of considerable concern, but they cannot
be fully corrected except with simultaneous prevention of further addition
of domestic and industrial waste discharges.
E-64
-------
TABLE E-10
WATER QUALITY AND FISH MORTALITY DATA OF THE THREE
EXPERIMENTS OF MUMMICHOGS SUBJECTED TO THE SOLUTION
OF BALTIMORE HARBOR SEDIMENT, STATION 10
Exp.
no.
I
1
1
1
1
1
2
2
3
3
3
2
.2
3
3
2
Suspended
solids
9/1
0.1
87.04
52.28
31.07
18.20
16.35
10.64
9.62
8.94
7.18
5.43
6.91
5.05
3.99
3.28
2.36
Dissolved
solids
9/1
5.40
6.43
5.92
5.15
6.10
5.96
5.64
5.26
5.81
5.72
5.43
5.31
4.82
5.83
5.74
4.64
Total
solids
9/1
5.5
93.47
58.20
36.22
24.30
11.6
16.28
15.88
14.75
12.90
10.86
12.22
9.87
7.82
9.02
7.00
Fish
Mortality
Turbidity
JTU
4
43,500
28,000
18,400
9,100
—
6,900
5,800
6,500
5,250
4,250
4,350
3,300
3,500
2,650
1,500
pH
8.3
5.0
4.75
4.8
4.65
5.0
5.2
5.75
4.8
4.9
5.8
6.02
6.5
6.6
7.0
7.1
DO
mg/1
7.2
4.5
6.5
6.5
6.5
6.35
6.4
5.7
6.6
6.5
6.6
6.6
6.6
6.6
6.5
6.5
%
24-hrs
0
100
100
100
100
100
80
70
50
40
10
0
0
0
0
0
48-hrs
0
100
100
100
100
100
100
100
70
60
20
0
0
0
0
0
E-65
-------
TABLE E-ll
WATER QUALITY AND FISH MORTALITY DATA OF THE TWO
EXPERIMENTS OF MUMMICHOGS SUBJECTED TO THE SOLUTION
OF BALTIMORE HARBOR SEDIMENT, STATION 8
Exp.
No.
7
7
7
7
6
6
6
6
6
6
7
Suspended
solids
9/1
34.78
23.65
IS. 70
15.27
12.20
10.57
8.80
7.96
7.56
0.08
0.01
Dissolved
solids
9/1
7.02
7.22
7.16
7.03
7.31
6.94
6.79
7.02
6.89
6.92
6.55
Total
solids
9/1
41.80
30.47
23.86
22.30
19.51
17.51
15.59
14.98
14.45
7.00
6.56
Fish Mortality
Turbidity
JTU
29,000
25,000
16,750
15,000
9,250
8,5OO
7,200
6,750
6,450
2
2
PH
4.8
5.2
5.3
5.3
5.9
5.6
5.8
5.8
6.0
8.2
8.1
DO
mg/1
6.8
7.4
7.4
7.4
7.5
7.1
7.7
7.6
7.6
7.9
7.5
%
24-hrs
100
20
20
0
0
0
0
0
0
0
0
48-hrs
100
50
30
10
0
0
0
0
0
0
0
E-66
-------
TABLE E-12
WATER QUALITY AND FISH MORTALITY DATA OF THE TWO
EXPERIMENTS OF MUMMICHOGS SUBJECTED TO THE SOLUTION
OF BALTIMORE HARBOR BOTTOM SEDIMENT, STATION 7
Exp.
No.
11
11
11
11
10
10
10
10
10
11
10
Suspended
solids
g/i
117.69
86.37
74.14
61.96
61.50
48.54
41.92
26.32
15.41
7.39
0.08
Dissolved
solids
9/1
5.54
6.71
6.70
7.58
6.05
6.27
6.59
6.47
6.40
6.20
6.82
Total
solids
9/1
123.23
93.08
82.84
69.54
67.54
54.81
48.51
32.79
21.81
13.59
6.90
Fish Mortality
Turbidity
JTU
66,000
64,500
58,000
55,000
45,500
37,500
32,500
23,500
15,000
5,800
2
pM
5.9
5.3
5.3
5.5
6.1
5.7
5.7
5.7
5.9
6.8
7.4
DO
mg/1
0.7
6.3
5.4
5.6
5.6
5.9
6.0
6.6
6.6
7.0
6.2
24-hrs
100
90
50
30
10
0
0
0
0
0
0
%
48-hrs
100
80
80
50
30
0
0
0
0
0
0
E-67
-------
TABLE E-13
WATER QUALITY AND FISH MORTALITY DATA OF TWO
EXPERIMENTS OF MUMMICHOGS SUBJECTED TO THE SOLUTION
OF BALTIMORE HARBOR SEDIMENT, STATION 6
Exp.
No.
9
9
9
9
12
12
12
12
12
9
12
Suspended
solids
9/1
71.26
58.93
47.08
34.91
31.34
27.38
21.05
20.39
17.74
0.08
0.05
Dissolved
solids
9/1
6.73
7.18
6.99
6.97
6.95
6.89
6.95
7.21
6.87
6.82
7.05
Total
solids
9/1
77.99
66.11
54.07
41.88
38.29
34.27
28.00
27.60
24.61
6.90
7.10
Fish Mortality
Turbidity
JTU
50,500
44,000
35,000
28,500
28,500
25,500
18,000
19,000
16,000
2
3
PH
5.0
5.0
5.1
5.2
5.5
5.7
5.4
5.9
5.9
7.4
7.5
DO
mg/1
5.1
5.3
6.2
6.2
7.5
7.3
6.2
7.4
7.4
6.2
7.3
24-hrs
100
100
100
90
70
60
30
20
0
0
0
%
48-hrs
100
100
100
100
90
80
30
40
0
0
0
E-68
-------
TABLE E-14
WATER QUALITY AND FISH MORTALITY DATA OF THREE
EXPERIMENTS OF MUMMICHOGS SUBJECTED TO THE SOLUTION
OF BALTIMORE HARBOR SEDIMENT. STATION 5
Exp.
No.
14
14
15
15
15
15a
15
15a
15a
15a
14
15
15a
14
Suspended
solids
9/1
3.36
3.10
2.34
2.21
1.44
1.44
1.40
1.13
0.92
0.77
0.48
0.38
-0.08
0.09
Dissolved
solids
g/i
7.46
7.42
6.87
6.87
6.87
6.85
7.11
6.87
7.12
6.76
7.02
7.26
7.20
6.37
Total
solids
g/i
10.82
10.52
9.21
9.08
8.31
8.39
8.51
8.00
8.04
7.63
7.80
7.64
7.12
6.49
Fish Mortality
Turbidity
JTU
3,000
2,750
2,700
2,400
1,800
1,800
1,400
-
1,300
1,100
590
465
6.5
3
pH
4.2
4.2
3.8
4.7
5.0
5.0
6.2
6.2
5.6
6.4
6.9
6.5
7.5
7.5
DO
mg/1
6.5
6.5
6.5
6.6
6.5
6.5
6.5
6.5
6.6
6.5
6.75
6.6
6.6
6.5
2 4-hr s
100
100
100
100
100
100
90
100
80
50
0
0
0
0
%
48-hrs
100
100
100
100
100
100
100
100
90
70
0
0
0
0
E-69
-------
TABLE E-15
WATER QUALITY AND FISH MORTALITY DATA OF TWO
EXPERIMENTS OF MUMMICHOGS SUBJECTED TO THE SOLUTION
OF BALTIMORE HARBOR SEDIMENT, STATION 9
Exp.
No.
8
5
5
4
4
5
5
4
5
4
4
5
4
Suspended
solids
9/1
33.79
16.95
15.02
14.32
13.09
11.46
11.09
10.99
8.77
8.60
7.01
0.10
0
Dissolved
solids
9/1
9.02
8.00
8.03
7.00
6.90
7.70
7.58
6.85
7.44
6.50
6.76
6.61
6.54
Total
solids
9/1
42.81
24.95
23.09
21.32
19.92
19.16
18.67
17.85
16.21
15.10
13.77
6.72
6.54
Fish Mortality
Turbidity
JTU
19,000
8,300
7,450
6,900
5,850
5,400
4,450
5,250
4,400
4,350
3,550
3.7
2.5
pH
9.0
8.9
8.9
9.3
9.3
8.9
9.3
9.3
8.9
9.3
9.2
8.2
8.2
DO
mg/1
5.6
7.5
7.7
8.3
8.2
7.7
7.8
8.4
8.9
8.2
8.2
9.2
8.3
24-hrs
20
0
0
20
10
0
0
10
0
20
10
0
0
%
48-hrs
30
0
0
50
70
10
10
20
0
30
20
0
0
E-70
-------
TABLE E-16
WATER QUALITY AND FISH MORTALITY DATA OF AN
EXPERIMENT OF MUMMICHOGS SUBJECTED TO THE SOLUTION
OF BALTIMORE HARBOR SEDIMENT, STATION 4
Exp.
no.
18
18
18
18
18
18
16
Suspended
solids
g/1
8.09
4.93
3.74
2.68
2.08
0.81
-0.25
Dissolved
solids
g/1
5.65
7.21
6.91
7.33
7.01
7.02
6.73
Total
solids
g/1
13.74
12.05
10.70
10.00
8.59
7.83
6.48
Fish Mortality
Turbidity
JTU
9,000
4,300
3,200
2,300
1,800
565
2.5
PH
5.2
5.7
6.0
6.3
6.75
7.2
7.6
DO
mg/1
6-9
7.1
7.1
7.0
7.0
7.0
7.1
%
24 hrs.
100
60
20
0
0
0
0
48 hrs
100
90
50
0
0
0
0
E-71
-------
TABLE E-17
WATER QUALITY AND FISH MORTALITY DATA OF TWO
EXPERIMENTS OF MUMMICHOGS SUBJECTED TO THE SOLUTION
OF BALTIMORE HARBOR SEDIMENT, STATION 2
Exp.
No.
16
20
20
20
20
20
16
16
16
16
16
Suspended
solids
g/1
20.94
10.48
9.41
8.43
7.58
6.70
4.94
3.82
2.45
1.19
-0.26
Dissolved
solids
g/1
7.66
6.95
6.16
7.26
6.78
7.08
7.05
7.00
7.02
'6.98
6.51
Total
solids
g/1
28.60
17.43
15.57
15.69
14.36
13.78
13.99
10.82
9.50
8.17
6.25
Fish Mortality
Turbidity
JTU
17,000
6,000
5,700
5,400
4,800
4,200
3,400
2,700
1,800
740
3
pH
4.2
4.4
4.4
4.4
4:6
4.9
5.7
6.0
6.75
7.2
7.5
DO
mg/1
6.1
6.5
6.5
6.6
6.6
6.7
6.5
6.5
6.5
6.5
6.6
%
24 hrs.
100
100
100
100
80
70
50
0
0
0
0
48 hrs
100
100
100
100
100
80
70
0
0
0
0
E-72
-------
TABLE E-18
WATER QUALITY AND FISH MORTALITY DATA OF THE THREE
EXPERIMENTS OF MUMMICHOGS SUBJECTED TO THE SOLUTION
OF BALTIMORE HARBOR SEDIMENT, STATION 1
Exp.
No.
17
21
21
21
21
24
24
24
24
17
17
17
17
17
21
Suspended
solids
g/1
21.14
22.41
18.43
17.10
13.92
11.08
9.29
8.56
7.38
5.01
3.54
2.60
2.14
0.79
- 0.06
Dissolved
solids
g/1
6.22
7.82
7.61
7.43
7.46
7.55
7.55
7.64
7.50
6.91
7.04
6.96
7.07
7.01
6.97
Total
solids
g/1
27.36
30.23
26.04
24.53
21.38
18.58
16.83
16.20
14.90
11.96
10.57
9.56
9.30
7.80
6.91
Fish Mortality
Turbidity
JTU
20,000
16,000
14,000
12,000
8,000
6,650
5,850
5.250
4,850
3,700
2,750
2,150
1,600
565
3
PH
4.5
4.5
4.6
4.6
4.7
5.9
5.8
5.9
6.2
6.5
6.7
6.8
7.2
7.6
7.8
DO
mg/1
6.0
6.2
6.2
6.5
6.6
6.6
6.9
6.9
6.7
6.9
6.9
7.0
6.9
6.7
6.7
24-hrs
100
100
100
100
100
40
30
10
10
0
0
0
0
0
0
&
48-hrs
100
100
100
100
100
60
60
40
10
0
0
0
0
0
0
E-73
-------
TABLE E-19
WATER QUALITY AND FISH MORTALITY DATA
OF THE THREE EXPERIMENTS OF MUMMICHOGS
EXPOSED TO FULLER'S EARTH SOLUTION
Exp.
No.
26
26
26
26
26
25
25
25
25
23
23
23
23
23
25
23
26
Suspended
solids
9/1
123.45
114.15
104.14
97.82
77.33
61.05
49.16
42.15
24.57
26.25
19.48
16.33
14.90
11.98
0.04
0
0.04
Dissolved
solids
9/1
9.95
9.18
8.10
9.20
9.41
9.78
9.65
9.62
9.69
8.44
8.44
8.37
8.29
8.28
9.39
8.79
9.34
Total
solids
9/1
133.40
123.33
121.24
107.02
86.74
71.83
58.81
51.77
34.26
34.69
27.92
24.70
23.19
0.26
9r43
8.79
9.38
Fish Mortality
Turbidity
JTU
31,000
25,000
25,000
29,500
21,000
17,000
15,000
12,000
5,950
5,650
4,600
4,400
3,700
3,150
3
2
2
PH
7.3
7.6
7.7
7.5
7.6
7.3
7.6
7.7
7.9
7.8
7.9
7.9
7.9
8.0
8.1
7.9
7.9
DO
mg/1
5.3
5.1
5.9
6.1
7.2
6.5
7.0
7.3
7.1
7.3
7.4
7.5
7.5
7.1
7.4
7.1
7.5
24-hrs
90
70
20
20
10
0
0
0
0
0
0
0
0
0
0
0
0
%
48-hrs
100
70
60
30
10
0
0
0
0
0
0
0
0
0
0
0
0
E-74
-------
TABLE E-20
WATER QUALITY AND FISH MORTALITY DATA
OF THE FOUR EXPERIMENTS ON SPOT
EXPOSED TO FULLER'S EARTH SOLUTION
Exp.
No.
29
29
29
35
29
35
36
36
36
35
35
36
27
27
Suspended
solids
9/1
122.06
98.84
77.20
75.08
74.73
74.48
70.30
67.89
66.48
64.34
51.52
49.60
26.37
-0.01
Dissolved
solids
9/1
9.63
9.18
8.70
10.69
8.43
9.82
11.31
11.79
12.06
10.90
9.78
10.70
9,73
9.29
Total
solids
131.69
108.02
85.90
85.76
83.57
84.30
81.61
79.67
78.54
75.24
61.30
60.30
18.05
9.28
Fish Mortality
Turbidity
JTU
33,000
26,000
24,000
23,000
24,000
21,000
25,000
27,000
26,000
20,000
16,000
20,000
6,100
2
DO
mg/1
5.6
5.5
5.5
6.5
6.2
6.3
5.9
5.4
6.6
6.3
6.1
6.1
6.9
7.2
pH
7.4
7.7
7.6
7.5
7.7
7.6
6.5
7.4
7.5
7.7
7.7
7.5
7.9
8.1
24-hrs
100
100
100
100
90
100
90
70
80
80
50
50
0
0
%
48-hrs
100
100
100
100
100
100
90
70
80
80
50
50
0
0
E-75
-------
TABLE E-21
WATER QUALITY AND FISH MORTALITY DATA
OF THE TWO EXPERIMENTS ON SPOT EXPOSED TO THE
SOLUTION OF BALTIMORE HARBOR SEDIMENT, STATION 10
Exp.
No.
30
30
32
30
32
30
30
32
32
32
Suspended
solids
g/i
17.30
15.75
10.30
8.74
6.67
6.38
2.71
6.30
4.11
-0.23
Dissolved
solids
9/1
8.66
8.56
8.24
8.71
7.67
8.61
8.60
7.59
7.84
8.96
Total
solids
9/1
25.97
23.78
18.54
18.45
14.33
14.97
11.31
13.90
11.95
8.73
Fish Mortality
Turbidity
JTU
12,500
9,000
6,200
6,000
4,800
3,975
1,375
4,500
3,350
2
DO
6.6
6.7
7.2
6.9
7.4
6.8
7.2
6.7
7.2
7.5
PH
5.3
4.9
5.6
5.2
5.6
5.9
7.4
5.9
6.5
8.1
%
24-hrs
100
100
90
30
0
0
0
0
0
0
48-hrs
100
100
100
60
3-0
0
0
0
0
0
E-76
-------
TABLE E-22
WATER QUALITY AND FISH MORTALITY DATA
OF THE TWO EXPERIMENTS ON SPOT SUBJECTED TO THE
SOLUTION OF BALTIMORE HARBOR SEDIMENT, STATION 8
Exp.
No.
31
31
31
31
34
34
34
34
34
31
31
Suspended
solids
9/1
53.93
46.68
29.29
21.97
20.39
17.46
16.60
16.53
15.79
14.09
0.25
Dissolved
solids
g/i
8.68
8.82
8.07
8.42
10.02
9.27
9.31
9.70
9.24
8.34
8.15
Total
solids
9/1
62.61
55.50
32.36
30.39
30.41
26.73
25.91
27.23
25.03
22.43
8.30
Fish Mortality
Turbidity
JTU
39,500
36,500
26,500
19,000
18,500
17,000
14,750
15,250
14,500
12,000
2
DO
5.9
6.6
6.1
6.6
6.8
5.3
5.5
5.5
6.4
5.5
6.6
PH
4.4
4.5
4.7
5.0
5.2
5.3
5.4
5.5
5.6
5.5
8.0
%
24-hrs.
100
100
100
100
80
20
10
10
0
0
0
48-hrs
100
100
100
100
90
40
20
40
40
0
0
E-77
-------
TABLE E-23
WATER QUALITY AND FISH MORTALITY DATA
OF THE TWO EXPERIMENTS ON SPOT EXPOSED TO THE
SOLUTION OF BALTIMORE HARBOR SEDIMENT STATION 7
Exp.
No.
38
38
38
38
38
39
39
39
39
Suspended
solids
9/1
38.25
36.76
31.67
29.31
27.81
21.19
14.79
12.87
7.74
Dissolved
solids
9/1
10.42
10.98
10.63
10.43
10.20
9.86
9.96
10.14
9.94
Total
solids
9/1
48.67
47.74
42.30
39.74
38.01
31.05
24.75
23.01
17.68
Fish Mortality
Turbidity
JTU
36,500
33,500
29,000
27,000
26,000
17,500
14,500
13,000
9,000
DO
6.7
6.6
6.8
6.6
6.7
6.1
6.5
6.5
5.8
PH
5.4
5.4
5.5
5.5
5.6
5.4
5.9
6.3
6.1
i
24-hrs
90
90
60
20
0
0
0
0
0
fc
48-hrs
100
90
90
20
0
10
0
0
0
E-78
-------
TABLE E-24
WATER QUALITY AND FISH MORTALITY DATA
OF THE TWO EXPERIMENTS ON SPOT EXPOSED TO THE
SOLUTION OF BALTIMORE HARBOR SEDIMENT, STATION 6
Exp.
No.
40
40
39
40
40
39
39
39
39
Suspended
solids
9/1
36.10
31.46
28.57
27.66
24.69
21.19
14.79
12.87
7.74
Dissolved
solids
g/i
10.95
10.62
9.89
10.43
10.44
9.86
9.96
10.14
9.94
Total
solids
9/1
47.05
42.08
38.46
38.09
35.13
31.05
24.75
23.01
17.68
Fish Mortality
Turbidity
JTU
26,000
25,000
25,000
24,000
21,500
17,500
14,500
13,000
9,000
DO
5.6
6.1
6.0
6.6
6.5
6.1
6.5
6.5
6.1
PH
5.1
5.2
5.3
5.2
5.4
5.4
5.9
6.3
5.8
24-hr.
100
100
80
60
50
0
0
0
0
48 -hr.
100
100
90
70
50
10
0
0
0
E-79
-------
TABLE E-25
WATER QUALITY AND FISH MORTALITY DATA OF THE EXPERIMENTS WITH SPOT
SUBJECTED TO THE SOLUTION OF BALTIMORE HARBOR SEDIMENT, STATION 5
00.
o
Expt.
No.
43
43
43
43
43
45
45
45
51
45
Suspended
Solids
9/1
2.13
1.96
1.66
1.63
1.43
1.02
0.99
0.89
0.62
0.57
Dissolved
Solids
g/i
11.28
11.32
11.12
10.96
11.00
22.06
11.04
7.02
13.46
11.14
Total f
Solids'
9/1
13.41
13.28
12.78
12.59
12.43
12.08
12.03
7.90
14.08
11.71
Turbidity
JTU
1700
1500
1300
1275
975
780
1100
950
545
678
PH
5.9
5.7
5.6
5.7
5.7
5.9
5.8
5.8
6.5
6.2
DO
6.5
6.6
7.0
7.1
7.5
6.1
6.6
6.5
6.2
6.6
Fish Mortal
24-hrs
100
100
100
100
100
100
100
90
10
0
ity %
48-hrs
100
100
100
100
100
100
100
100
60
0
-------
TABLE E-26
WATER QUALITY AND FISH MORTALITY DATA OF AN EXPERIMENT WITH SPOT
SUBJECTED TO THE SOLUTION OF BALTIMORE HARBOR SEDIMENT, STATION 4
Expt.
No.
52
52
M
1
oo 52
52
52
Suspended
Solids
9/1
10.04
6.90
6.41
5.92
4.05
Dissolved
Solids
g/i
11.18
11.53
11.47
11.72
12.13
Total
Solids
9/1
21.22
18.43
17.88
17.64
16.18
Turbidity
JTU
7700
6100
5500
5250
4000
PH
4.7
4.8
5.1
5.7
5.6
DO
mg/1
6.1
6.2
6.4
6.0
6.5
Fish Mortal
24-hrs
100
100
100
10
0
ity %
48-hrs
100
100
100
10
0
-------
TABLE E-27
WATER QUALITY AND FISH MORTALITY DATA OF THREE! EXPERIMENTS WITH SPOT
SUBJECTED TO THE SOLUTION OF BALTIMORE HARBOR SEDIMENT, STATION 2
Expt.
No.
46
46
46
H
co 46
tv
49
49
42
42
42
Suspended
Solids
g/i
8.41
7.47
7,34
6.01
5.83
5.61
3.53
2.38
1.03
Dissolved
Solids
g/i
11.77
11.59
11.87
11.39
12.08
11.77
10.82
10.48
1.073
Total
Solids
g/i
20.18
19.06
19.21
17.40
17.91
17.38
14.35
12.86
11.76
Turbidity
JTU
5300
5100
4900
4450
4650
4200
2550
1600
900
PH
5.4
5.3
5.5
5.5
6.0
6.0
6.6
6.8
7.1
DO
6.5
6.4
6.5
6.3
6.6
6.3
6.9
6.7
6.8
Fish Mortal
24-hrs
100
90
80
80
60
50
0
0
0
ity %
48 hrs
100
100
100
90
90
70
0
0
0
-------
TABLE E-28
CO
OJ
WATER QUALITY AND FISH MORTALITY DATA OF TWO EXPERIMENTS WITH SPOT
SUBJECTED TO THE SOLUTION OF BALTIMORE HARBOR SEDIMENT, STATION 1
Expt.
No.
47
50
50
50
47
47
50
50
Suspended
Solids
9/1
13.66
11.23
9.77
8.99
7.91
6.13
6.28
4.48
Dissolved
Solids
g/i
10.49
10.79
11.41
10.81
9.42
10.31
11.09
9.13
Total
Solids
9/1
24.15
22.02
21.18
19.80
17.40
16.44
17.37
13.61
Turbidity
JTU
8200
7350
6550
5800
5200
4200
4000
3700
PH
5.6
6.0
6.2
6.5
6.1
6.9
6.5
6.9
DO
6.4
6.8
7.1
6.9
6.6
6.9
6.8
7.1
Fish Mortal
24-hrs
100
100
70
30
20
10
0
0
ity %
48 hrs
100
100
80
30
20
20
0
0
-------
TABLE E-29
WATER QUALITY AND CLAM MORTALITY DATA OF THE EXPERIMENTS
WITH SOFT-SHELL CLAMS SUBJECTED TO THE SOLUTION
OF BALTIMORE HARBOR SEDIMENT, STATION 1
Expt.
No.
62
62
H
OD 59
62
59
62
Suspended
Solids
g/1
129.51
106.27
39.09
33.32
16.04
0.14
Dissolved
Solids
g/1
15.59
14.88
13.17
13.81
13.28
12.50
Total
Solids
9/1
145.10
121.15
52.26
47.13
29.32
12.64
Turbidity
JTU
67,000
57,000
29,000
27,000
13,500
2
PH
4.3
4.3
5.0
4.9
6.4
7.5
DO
3.4
6.1
7.1
7.5
7.1
6.3
Clam Mortal
24-hrs
30
10
0
10
0
0
ity %
48 hrs
50
40
20
30
0
0
-------
TABLE E-30
WATER QUALITY AND CLAM MORTALITY DATA OF EXPERIMENTS
WITH SOFT-SHELL CLAMS SUBJECTED TO THE SOLUTION
OF BALTIMORE HARBOR SEDIMENT, STATION 2
Expt.
No.
58
57
W 58
oo
^ 57
58
58
58
Suspended
Solids
9/1
49.49
49.20
48.25
47.33
34.11
17.00
-0.02
Dissolved
Solids
g/i
13.15
12.36
13.12
12.28
12.12
12.07
11.05
Total
Solids
g/i
62.64
61.56
61.37
59.61
46.23
29.07
11.03
Turbidity
JTU
34,000
32,000
31,000
30,750
25,000
13,000
4
PH
4.6
4.3
4.8
4.4
5.0
5.3
7.4
DO
6.5
5.2
6.5
5.8
6.4
6.8
6.8
Clam Mortal
24-hrs
50
50
30
40
30
10
0
ity %
48-hrs
100
90
80
90
100
50
0
-------
TABLE E-31
WATER QUALITY AND CLAM MORTALITY DATA OF EXPERIMENTS
WITH SOFT-SHELL CLAMS SUBJECTED TO THE SOLUTION
OF BALTIMORE HARBOR SEDIMENT, STATION 4
Expt.
No.
60
61
H
k 6°
60
61
cZ
Suspended
Solids
9/1
39.40
38.06
37.87
23.69
22.21
0.14
Dissolved
Solids
9/1
12.50
13.50
12.13
11.79
12.45
12.50
Total
Solids
9/1
51.90
51.56
50.00
35.48
34.66
12.64
Turbidity
JTU
35,000
34,000
35,000
21,500
20,500
2
PH
3.9
4.8
3.8
4.9
5.2
7.5
DO
6.6
6.1
6.2
6.8
7.0
6.3
Clarn Mortal
24-hrs
10
40
10
10
0
0
ity %
48-hrs
50
40
40
50
30
0
-------
H
i
oo
TABLE E-32
WATER QUALITY AND CLAM MORTALITY DATA OF TWO EXPERIMENTS
WITH SOFT-SHELL CLAMS EXPOSED TO THE SOLUTION
OF BALTIMORE HARBOR SEDIMENT, STATION 5
Exp.
noo
70
70
70
63
70
63
70
63
70
Suspended
solids
g/I
66.86
45.09
30.15
22.13
19.85
10.74
8.72
0.10
0.06
Dissolved Total
solids solids
g/1
20.82
18025
I5o96
14.39
14.61
12.47
13.01
11.42
12.14
g/1
87.68
63.38
46.11
36.52
34.46
23.21
21.73
11.52
12.20
Turbidity pH
JTU
54,000
35,000
27,000
20,000
17,500
10,000
6,050
3
3
3.5
3.6
3.8
4.2
3.5
3.7
4.5
7.5
7.8
DO
mg/1
4.8
6.3
7.5
5.7
7.4
6.3
7.7
8.0
7.5
Clam mortality($)
24 hrs
80
60
50
40
40
30
20
0
0
48 hrs
90
80
100
80
90
80
90
0
0
-------
w
I
oo
TABLE E-33
WATER QUALITY AND CLAM MORTALITY DATA OF TWO EXPERIMENTS
WITH SOFT-SHELL CLAMS EXPOSED TO THE SOLUTION
OF BALTIMORE HARBOR SEDIMENT, STATION 6
Exp.
no.
Suspended
solids
g/1
74
67
74
67
67
67
150.
139.
135.
131.
130.
- 0.
75
77
4l
94
05
07
Dissolved Total
solids solids
g/1
13.53
11.61
12.95
11.4o
11.33
12.39
g/1
164.28
151.38
148.36
143.34
141.38
12.32
Turbidity pH
JTU
91,000
100,000
95.500
87,000
81,000
2
4.2
4.3
4.4
4.3
4.3
7.6
DO -
mg/1
6.4
6.6
6.8
7.8
5.1
7.4
Clam mortality (%)
24 hrs 48 hrs 72 hrs 96 hrs
0
0
0
0
0
0
40
10
40
0
0
0
60
20
80
10
20
0
100
100
100
100
100
0
-------
H
i
CO
TABLE E-34
WATER QUALITY AND CLAM MORTALITY DATA OF TWO EXPERIMENTS
WITH SOFT-SHELL CLAMS EXPOSED TO THE SOLUTION
OF BALTIMORE HARBOR SEDIMENT, STATION 7
Expo
no.
77
77
85
72
85
68
85
77
Suspended Dissolved Total
solids solids solids
g/1
173.21
167.21
1^7.26
137.71
121.75
108.82
103.61
0.06
£/l
13.97
13.14
14.67
11.69
16.58
10.86
12.79
12.14
g/1
187.18
180.35
161.93
149.40
138.33
119.28
io6.4o
12.20
Turbidity
pH
JTU
175
150
150
98
94
77
75
,000
,000
,000
,500
,000
,000
,000
3
4.7
4.8
4.9
4.7
4.8
4.8
4.9
7.8
DO
mg/1
6.6
6.5
6.5
6.1
606
7.2
6.3
7.5
Clam mortality ($)
24 hrs 48 hrs 72 hrs 96 hrs
0
0
0
0
0
0
0
0
30
60
30
20
0
0
0
0
100
100
100
50
50
20
10
0
100
100
100
100
100
60
60
0
-------
H
^
o
TABLE E-35
WATER QUALITY AND CLAM MORTALITY DATA OF TWO EXPERIMENTS
WITH SOFT-SHELL CLAMS EXPOSED TO THE SOLUTION
OF BALTIMORE HARBOR SEDIMENT, STATION 8
Exp0
uoe
76
76
76
69
69
76
Suspended Dissolved Total
solids solids solids Turbidity jJfi
g/1
113.80
101.98
96.15
84.39
68.42
0.06
g/1
13.34
13.23
13.09
10.88
8.64
12.14
g
127.
115.
109.
95.
77.
12.
;/i
14
21
24
27
06
21
JTU
85,000
73,ooo
70,000
68,000
52,500
3
4.7
4.4
4.5
4.5
4.7
7.8
DO
mg/1
6.8
6.2
6.4
6.5
6.7
7,5
Clam mortality ($)
24 hrs 48 hrs 72 hrs 96 hrg
10
20
0
0
0
0
60
40
20
0
0
0
100
90
70
0
0
0
100
100
100
20
40
0
-------
w
TABLE E-36
WATER QUALITY AND CLAM MORTALITY DATA OF TWO EXPERIMENTS
WITH SOFT-SHELL CLAMS EXPOSED TO THE SOLUTION
OF BALTIMORE HARBOR SEDIMENT, STATION 10
Exp0
nOo
80
80
81
8l
81
8l
Suspended
dolids
S/l
156o48
152.39
150.8?
lM.91
132.39
0.25
Dissolved Total
solids solids
g/1
14.28
16. 03
15.66
14.48
13.8?
13.34
g/1
170,76
168.42
166.53
159.39
l46026
13.59
Turbidity pH
JTU
97,000
81,000
83,000
83,500
75,000
2
3.8
3.8
3.8
3.8
3.9
7.4
DO •
mg/1
6.0
5.8
5.6
5.7
5.4
7.7
Clam mortality (.%}
24 hrs 48 hrs 72 hrs
40
20
30
30
0
0
80
90
90
70
60
0
100
100
100
90
100
0
-------
xO
TABLE E-37
WATER QUALITY AND CLAM MORTALITY DATA OF THREE EXPERIMENTS
WITH SOFT-SHELL CLAMS EXPOSED TO SOLUTION OF FULLER'S EARTH
Exp.
noo
78
86
78
83
83
78
78
86
86
Suspended
solids
g/1
202,
176.
144.
127.
1240
119.
78.
66.
0.
07
43
55
85
61
09
68
99
02
Dissolved Total
solids solids Turbidity pH
g/1
10o32
11.76
10.23
12.21
12.09
10.28
10.17
11.21
11.19
g/1
212.39
188.19
154.78
140.06
136.70
129.37
88085
78.20
11.21
JTU
53,000
44,000
36,000
38,500
41,000
28,250
22.250
23.500
2
7.2
7.3
7.3
6.4
7.2
7.4
7.5
7.4
7*3
DO
mg/1
3.8
2.0
5.1
6.3
6.0
7.4
7.0
5.3
8.0
Clam mortality (%}
24 hrs 48 hrs 72 hrs 96 hrs
0
0
0
0
0
0
0
0
0
10
20
0
0
0
0
0
0
0
40
30
30
20
10
20
0
0
0
90
40
90
60
20
90
10
20
0
-------
APPENDIX F
SUPPLEMENTARY DATA ON DREDGING, DISPOSAL,
AND BLANKETING TECHNIQUES
-------
F. 1 DREDGING AND DISPOSAL
One of the more important recent investigations of the effects of dredging
in an estuarine environment is a detailed study of the effects of dredging
and disposal in the San Francisco Bay and Estuary by the U. S. Army
Corps of Engineers. This study, as reported in July 1975, reached
a number of conclusions. Those which are most important to an under-
standing and consideration of dredging and spoil disposal results of the
San Francisco study final composite environmental statement are quoted
below:
"The purpose of this Statement of Findings is to set forth the
rationale leading to a recommendation that the maintenance
dredging for the Federal navigation projects in San Francisco
Bay be continued as authorized, and as described in the Final
Composite Environmental Statement".
"3. Rationale and Discussion. The possible consequences of
the navigation projects have been studied for environmental,
social well-being, economic effects (including regional and
national economic development) and engineering feasibility.
In evaluating the projects, the following points were considered
pertinent:
a. Environmental Considerations.
(1) Bay Estuary - Turbidity in the upper water column
from a dredging activity usually lasts less than 15 minutes with
the highest turbidity values adjacent to the dredge. In addition
to the turbidity plume created in the upper water column, dredg-
ing induces an ill-defined fluff zone in the channel bottom which
can last up to several weeks. This fluff zone shifts with the tide
but is localized to the channel boundaries, and eventually con-
solidates.
F-Z
-------
"Material released at open water disposal sites reaches
the bottom relatively intact. Less than five percent of the
material is dispersed in the upper water as the material des-
cends. The disposed sediments are subsequently dispersed
within the bottom few feet of the water column, diluted, and
follow the circulation pattern of natural sediment distribution
in the Bay.
Benthic organisms experience various amounts of dredging
impact depending on the surface area distributed, the numbers
and species present, depth of the cut, and frequency of mainte-
nance. In San Francisco Bay, it does not appear that sediments
from disposal operations cause extensive smothering of benthic
organisms because the disposal areas are high energy areas
where currents are swift and continuous. Estuarine fish (includ-
ing anadromous fish) are generally tolerant of relatively high
turbidity and can avoid or move away from immediate areas of
impact.
Dredging and disposal have adverse impacts on bottom dwel-
ling organisms in the immediate work areas. Some organisms
are destroyed at both the dredging and disposal site, while others
are transported to the disposal site. Indications are that, while
there is some diversity of life at project and disposal sites,
these areas, in general, do not have as great an abundance of
life as those areas outside the channel or disposal sites.
To date, there is no indication that dredge and disposal
operations directly influence uptake of toxic constituents although
there is evidence of limited release of some contaminants during
sediment agitation.
b. Social Well-Being Considerations.
(1) Historical and Archaeological Sites - All 20 projects
are areas previously dredged. Of the five projects involving land
disposal, only-the Port of Redwood City has tentatively chosen a
land disposal site. The site has been investigated by an archaeol-
ogist and the determination has been made that no archaeological
resources exist and that no historical sites will be affected. Any
other potential sites for Port of Redwood City land disposal and
F-3
-------
"land disposal sites for other projects will be surveyed by a pro-
fessional archaeologist, and a supplement to the environmental
statement will be issued to cover this and other considerations.
(2) Demography and Land Use - Most of the 20,400 port-
related jobs are in core urban areas and help sustain the economic
health of those areas. Maintenance dredging is essential to port
operations; thus it strengthens the inner city economies and to
some extent retards the exodus from cities to suburbs.
(3) Government - Port activities comprise a vital part
of socio-economic structures of city government land use plans.
(4) Transportation - Trucking and rail lines interface
with waterborne commerce in the Bay area to link water and land
freight transfer. Maintenance dredging serves to continue this
efficient and economical land-water freight system.
(5) Recreation Maintenance dredging benefits some
recreational boaters in areas such as San Rafael Creek and
San Leandro Marina as well as all other marinas covered under
Corps permit program. Cessation of maintenance dredging
would have a negative social impact on such recreation activities.
(6) Scenic Resources - Land disposal would have an
aesthetic impact. If land disposal is utilized, this impact will be,
assessed in the appropriate supplemental environmental statement.
c. Engineering Considerations.
(1) Existing Project The Federal navigation projects
under consideration have already been constructed. Hydrographic
surveys are routinely done to determine when maintenance dredging
is required and to estimate the amount of material to be dredged.
(2) Land Disposal - Those projects for which land dis-
posal is being considered v/ill be subjected to engineering review
and analysis. This review and analysis will consider such items
as seismic hazards, ground water, runoff, etc. Supplemental
environmental statements for these projects will include these con-
siderations .
F-4
-------
" (3) Future Projects - New dredging projects, both Federal
and private requiring a permit, and expansion of current projects
will be the subject of engineering review and analysis and will have
separate environmental reports issued on them.
d. Economic Considerations.
(1) Economy - Maintenance of Federal navigation projects
will have a positive impact on the San Francisco Bay regional econ-
omy. Dredging is considered to have beneficial long-term impacts
for maintaining port facilities and navigation commerce, helping
to maintain land values, public revenues, and the provision of com-
munity services. Total military and civil port investment in the
Bay-Delta area was nearly $2 billion through 1973. Over 4, 500
vessel trips with ships greater than 25-foot draft, requiring dredged
channels for navigation, passed through San Francisco Bay and over
56 million tons of cargo were handled in Bay-Delta ports in 1973.
(2) Employment - the Federal navigation projects maintain
channels that serve commercial ports, private wharves, oil piers,
and military installations that are dependent on Bay access. Approx-
imately 7; 800 jobs were related to export in the Bay area. Numerous
other jobs are indirectly related to waterborne transportation.
e. Alternative Considerations.
(1) No Maintenance - In order to provide open navigation
channels for commercial shipping and other purposes in the
national interest, dredging in the Bay area has become a continual
operation and it is doubtful that maintenance dredging would be
permanently halted. Two programs of decreasing maintenance
dredging activities, partial and complete moratoriums, would be
extreme measures having severe negative socio-economic impacts
throughout the Bay region and the nation, as well as both positive
and negative environmental effects.
(2) Alternate Dredging Methods - Present dredging methods
in the Bay include the hydraulic cutterhead pipeline, the hopper
dredge and the clamshell dredge. Each method is uniquely suited
for particular project conditions. Studies are being conducted to
develop methods which may reduce impacts on the aquatic environ-
ment without decreasing dredging efficiency. All methods are
required to meet the total dredging requirement.
F-5
-------
"(3) Alternate Disposal Sites - Alternative proposals for
disposal in the Bay are ocean disposal, land disposal, and salt
marsh development. Large scale ocean disposal by hopper and/or
barge is uneconomical and not in line with energy conservation. A
conceptual plan of a permanent, self-contained pipeline system to
the ocean disposal site was investigated for economic feasibility,
but appears infeasible in the short run. Any ocean disposal plan
would require a detailed study in which alternative ocean disposal
plans would be thoroughly assessed prior to approval. Land dis-
posal is a short-term alternative and should be considered as an
alternative to aquatic disposal. Should land disposal be selected
for'a particular project, a supplemental environmental statement
will be prepared covering all aspects of this alternative. Marsh
development studies have shown this to be a feasible alternative;
however, like other land disposal alternatives, it should be con-
sidered short-term and of limited applicability.
(4) Economic Consideration for Alternatives - Economic
analysis of the cost efficiency of alternative dredging and disposal
systems were derived in the following ranking (from least expen-
sive to most expensive): closest aquatic disposal (no constraints on
disposal), closest aquatic disposal seaward of the dredge site (no
constraints), ocean disposal (100-fathom contour), land disposal
(Petaluma River Area), delta island reclamation (Sherman Island),
and marshland development (Petaluma River Area).
(5) Reduce Shoaling Rate - Studies have been conducted
involving structural plans to either prevent shoaling in the navi-
gation channels or to increase flushing of the channels, and
selection of alternative aquatic disposal sites to reduce the amount
of sediments returning to the channels.
(6) Development in Dredging Technology - Important
factors being considered involve improving the efficiency of dredg-
ing techniques, acquiring new equipment, applying chemical addi-
tives, and adjusting the timing, scheduling, and methodology of
dredging operations. These factors are being studied by the Corps.
f. Other Public Interest Considerations.
(1) Federal Navigation Projects - Federal navigation projects
planned for the coming year are announced in a single public notice.
Revised public notices are issued as required.
F-6
-------
" (2) Regulatory Permit Actions - Dredging projects for
which a Department of the Army permit is required are announced
by public notice. For small volumes (less than 10,000 cubic yards)
involving land disposal above MHHW, no public notice is issued;
however, all concerned agencies are afforded the opportunity to
comment on the project.
(3) Public Hearings - If requested, public hearings are
held on both Federal navigation projects and permit dredging
projects. These hearings afford concerned agencies and individ-
uals additional opportunity to comment.
4. Conclusions and Recommendations. Based on an analysis and
evaluation of the investigation conducted on the proposed Federal
navigation projects, I find that an interdisciplinary approach has
been used in the preparation of the Final Composite Environmental
Statement and that all major environmental issues have been addres-
sed. I find that where the proposed projects have adverse environ-
mental effects, these effects are limited (based on available study
results), or are substantially outweighed by other positive con-
siderations. There are no adverse economic effects with regard
to these projects. On the contrary, there are substantial positive
economic benefits to be gained by the Bay Area, and a curtailment
of these maintenance projects could, in fact, have a major adverse
economic impact.
Therefore, based on a thorough analysis, and evaluation, I
recommend that the subject Federal navigation projects be main-
tained as authorized, with the understanding that land disposal will
be analyzed in supplements. I further recommend that the Final
Composite Environmental Statement be used to aid in assessing the
impacts of future permit navigation projects. I find this recommenda
tion consistent with national policies, statutes, and administration
directives.
/si H. A. Flertzheim
28 November 1975 H. A. FLERTZHEIM, JR.
Colonel, CE
District Engineer "
F-7
-------
F. 1. 1 Pneuma^ Dredge
The Pneumar^Dredge is a dredging and transport system which has been
developed by Pneuma International S. A. , an Italian firm. The dredge
design uses compressed air for pumping and uses hydrostatic pressure
to remove materials from the bottom. The system has been used in
most standard dredging applications and has achieved acceptance, partic-
ularly in stiuations involving the removal of sediments from channels and
harbor areas. It is claimed that very little sedimentation is caused by
the cutting and removal actions of the system. High percentages (60 -
90%) of solids are also reported.
The system uses three cylinders grouped together to form.a pump body.
Special valves for inlet and outlet are installed on each of the three
cylinders. A distributor functions to automatically control the supply of
compressed air to each cylinder and the exhaust of compressed air from
the cylinder to the atmosphere. When the pump body is submerged,
water fills the pump body after lifting the inlet valve in each cylinder due
to the hydrostatic head. The water, or the material to be dredged, enters
the pump body through an inlet tube which extends below the pump body
and to which may be attached various suitably shaped shovels. When the
pump body has been filled, the distributor supplies compressed air to
F-l
-------
the pump body. The inlet valve closes because the pressure inside the
pump body is now greater than the ambient hydrostatic pressure; and
the air pressure acts as a piston, forcing the material inside the pump
body out through a pipe which extends to the lower portion of the pump
body. When the cylinder has been almost emptied, the distributor vents
the air in the cylinder to the atmosphere and equalizes the cylinder
internal pressure with atmospheric. This naturally creates a pressure
differential between the inside of the cylinder and the hydrostatic pres-
sure. This pressure differential induces the flow of sedimentary mate-
rials through the inlet tube, lifting the inlet valve and refilling the cylinder.
In order to maintain a continuous flow rate, the distributor acts on the
three cylinders in turn, repeating the cycle described above.
Since there is little mechanical disturbance of the bottom sediments from
\\Ri
the action of the Pneuma Dredge, very little turbidity is produced.
This descriptive material was extracted from a "Test Report on Dredging
by S.I. R.S.I. Pneuma Pump System", from the abstracts of "The Japan
Dredger Technical Society", Number 82, July 1972, by Y. Takamura,
S. Kasajima and C. Mukai, all of the Port and Harbor Bureau, City of
Osaka.
F-9
-------
F.2 BLANKETING
Blanketing is a technique that has been used to control the turbidity
caused by the disturbance of sea-floor sediments. In some underwater
work, the reduction to visibility which may persist for some hours after
disturbance is a serious hindrance to continued work by divers. In order
to deal with this problem, local applications of plastic sheeting, the pour-
ing of hydraulic mortar and the formation on an in-place plastic film have
been explored. For one of the purposes of this study, the evaluation of
possible remedial actions to reduce or eliminate the impact of pollutants
upon the Harbor waters, it appeared valuable to pursue the possibilities
of a formed-in-place plastic layer. Successful placement of a plastic
layer couid offer two advantages: (1) preventing the disturbance of con-
taminated sediments and (2) isolation of the water column from the in-place
contaminated sediments.
A description of a process to form such a plastic film in place on the sea
bottom is contained in Technical Note N-1107, "Chemical Overlays for
Seafloor Sediments", by T. Roe, J. S. Williams and H. J. Migliore,
June, 1970, published by the Naval Civil Engineering Laboratory, Port
Hueneme, California. This Technical Note and United States patent num-
ber 3,845,003, granted to Thorndyke Roe, Jr., and assigned to United
F-10
-------
States of America as represented by the Secretary of Navy, provide the
basis for the information which follows.
The Technical Note and the patent describe the use of the following two
distinct film-forming chemical solutions, each of which precipitate when
extruded through a slit into sea water:
Parts by Weight
1 . Polyvinyl butyral resin 1.0
2-(2-ethoxyethoxy) ethanol 28.4
Citric acid 13.4
Dibutyl Phthalate 7. 9
Dimethyldicocoammonium chloride 75% active 0. 1
2. Polyvinyl butyral resin 1.0
2-(2-ethoxyethoxy) ethanol 24.6
Chlorinated Paraffins 12.0
Dibutyl Phthalate 6.0
Dimethyldicocoammonium chloride, 75% active 2. 1
In practice, these solutions have been found to provide a continuous flex-
ible non-toxic plastic film capable of covering the ocean floor sediment
F-ll
-------
and preventing the sediment from becoming disturbed and suspended in
the sea water. Also, these non-toxic plastic films were found to have a
strength sufficient to support light loads and a strength which increased
with deposit time.
Included in the solution is an antistatic agent to reduce the static electri-
city on the extruded plastic film. This enhances the spreading of the
plastic film by allowing the film to spread in thinner sheets than would
otherwise be possible. The antistatic agent utilized in the present inven-
tion is Dimethyldicocoammonium chloride, 75% active.
The other significant factor in the formulation is the use of a solvent which
itself is miscible and preferably soluble in sea water. Consequently, when
the solution initially is exposed to the sea water, the solvent commences to
dissolve in the sea water permitting the resin system to precipitate out in
a desired manner. The initial film formed by the precipitation is suffi-
ciently cohesive to provide a continuous sheet although the toughness or
strength of the sheet will not be achieved until the solvent has completely
dissolved in the water.
In the same period (1967-69) under contract to the Supervisor of Salvage,
U. S, Navy, Battelle Memorial Institute developed a two-component
F-12
-------
overlay method in which sodium alginate containing titanium dioxide as
a weighing agent is insolubilized by treatment with dilute hydrochloric
acid. The overlay formed instantly and had fair mechanical properties.
Its surface was quite slippery; and when walked upon, it tended to extrude
or creep out from under one's feet and break up. It had some resilience
and very low tensile strength. If a large area is to be covered, adjacent
layers of this material cannot be bonded to one another, but must be over-
lapped or cross-hatched. Because of its requirement for two components,
its marginal mechanical properties and its inability to bond to itself, this
method is not recommended for future development.
Pilot-test costs for these overlays were on the order of $1.00 per square
foot (1970).
Experimental runs of fixed-slit dispensers with candidate overlay solu-
tions were conducted in 25 feet of water off Santa Cruz Island and in 50
feet of water off Anacapa Island. These tests indicated that a chemical
overlay dispensing system could not be entirely diver-operated. Any
system which requires divers to swim above the sediment with a dispenser
and attached hose was found to be impractical because the dispenser and
hose are too cumbersome to be handled in this manner. For this reason,
F -13
-------
two dispensing system prototypes were proposed: one to be used on a
Construction Assistance Vehicle (CAV), and a subsequent model to be
used on a deep-water submersible.
The CAV provides a load bed that can support a dispensing-system
prototype. As the CAV cruises over an intended work site, the dis-
penser, suspended from the stern, can apply chemical overlay solution
on the sea floor. Several parallel runs, overlapped at the edges, would
completely cover the site. With the CAV in mind, the main features of
the chemical overlay dispensing system include: (1) 600-gallon capacity;
(Z) at least 100 square feet per minute and 2000 square feet per hour
coverage; (3) storage container to be pressure-compensated; and (4) stip.
ulations to ensure convenience and efficiency in operator control.
F-14
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F. 3 APPENDIX F - REFERENCES
U. S. Army Corps of Engineers, Final Composite Environmental
Statement, Maintenance Dredging, Existing Navigation Projects,
San Francisco Bay Region California, Volume 1, December 1975.
(Quoted in section F. 1)
APPENDIX A - Main Ship Channel (San Francisco Bar)
Study of the effects of dredging and disposal on the Bar outside of
the Golden Gate and consideration of optimal procedures.
APPENDIX B - Pollutant Distribution
Not yet available.
APPENDIX C - Water Column
Observations in the Bay of the effects of dredging and spoil place-
ment, with special attention to oxygen demand, suspended solids,
mounding or dispersal of deposits and the factors affecting these
characteristics.
APPENDIX D - Biological Community
Detailed survey of the distribution and abundance of infauna at
11 stations in San Francisco Bay and analysis of the heavy metal
content of the biota and of some environmental conditions.
APPENDIX E - Material Release
Not yet available.
APPENDIX F - Cyrstalline Matrix
Sediments from nine sites -were analyzed for physical, chemical,
and mineralogical parameters and the data were analyzed with
reference to implications for dredge-related activities. Many
components and conditions were included.
APPENDIX G - Physical Impact
Experimental evaluation of the effects of fine sediments in suspen-
sion and of cataclysmic deposition on estuarine macrofauna, with
interpretation in redredging activities. Experiments involved effect
of sediments, temperature,, of depressed oxygen concentrations
F-15
-------
and of simultaneous variation of all three. Includes the edible
mussel, young striped bass, a perch, sand shrimp, and others.
Good literature review.
APPENDIX H - Pollutant Uptake
Report on field experiments in which resident and transplanted
organisms were observed before, during, and after near-by dredg-
ing activity for heavy metal uptake and effects.
APPENDIX I Pollutant Availability
Results of an experimental placement of polluted sediments and
detailed observations on resident and transplanted benthic species.
APPENDIX J Land Disposal
Analysis of the economic, technical, and environmental aspects
of land placement of materials dredged from San Francisco Bay.
APPENDIX K - Marsh Development
Report on experimental efforts to create suitable habitat for marsh
development and encourage development of California cord grass,
Spartina foliosa, and pickleweed, Salicornia sp. Methods, costs,
and pollutants for San Francisco Bay are presented.
APPENDIX L- - Dredging Technology
Field observations and tank simulation of release patterns of various
types of sediment were analyzed to assist in predicting the mounding
or spreading and other attributes of the release pattern.
Biological Impacts of Suspensions of Dredged Material, Richard
Peddicord, U. S. Army Corps of Engineers, Waterways Experiment
Stations, Environmental Effects Laboratory, Vicksburg, Mississippi,
Paper presented at WODSON VII, World Dredging Conference, San
Francisco, California, July 10-12, 1976.
Effects of Suspended Solids on San Francisco Bay Organisms, R.
Peddicord, V. A. McFarland, D. P. Belfiori, T. E. Byrd,
University of California, Bodega Marine Laboratory, Bodega Bay,
California. Paper presented at WODCON VII, World Dredging
Conference, San Francisco, California, July 10-12, 1976.
F-16
-------
Applications of Predictive Sediment Transport Models, by R. B.
Krone, University of California, Davis, California, and C. R.
Ariathurai, Nielson Engineering and Research, Inc., Mountain
View, California.
Containment Area Facility Concepts for Dredged Material Separation,
Drying and Handling, by C. W. Mallory and M. A. Nawrocki of
Hittman Associates, Inc. , for the Dredged Material Research
Program of the Environmental Effects Laboratory of the U. S. Army
Corps of Engineers Waterways Experiment Station, Vicksburg,
Mississippi.
Identification of Relevant Criteria and Survey of Potential Appli-
cation Sites for Artificial Habitat Creation, Volume 1, Relevant
Criteria for March-Island Site Selection and Their Application,
by Coastal Zone Resources Corporation, Wilmington, North
Carolina, October 1975.
An Examination of some Physical and Biological Impacts of Dredging
in Estuaries, Interdisciplinary Studies of the Schools of Engineering
and Oceanography, Oregon State University, Corvallis, Oregon
submitted to the Division of Environmental Systems and Resources
(RANN), National Science Foundation, Washington, D. C. , NSF RANN
GRANT Gl 34346, December, 1974.
F-17
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APPENDIX G
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G-12
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APPENDIX H
ACKNOWLEDGEMENTS AND PARTICIPANTS
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H. 1
CONTRACT AND CONTRACTORS
This project was undertaken for the Environmental Protection Agency,
Toxic Substances Branch, 401 M Street, WSM, Washington, D. C. 20460,
under Contract No. WA 75 R263.
Contractor for the project was Trident Engineering Associates, Inc.,
48 Maryland Avenue, Annapolis, Maryland 21401, in conjunction with
the Center for Environmental and Estuarine Studies, University of Mary-
land, Horn Point, Cambridge, Maryland 21613.
Participants in the project were:
Trident Engineering
Mr. Richard H. Wagner
Dr. John F. Hoffman
Dr. Raymond P. Morgan, Jr.,
Chesapeake Biological Laboratory
Ms. Kristen K. Stout
Project Manager
Project Scientist
Trident Associate for
PCB Analysis
Biologist
H-2
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Center for Environmental
and Estuarine Studies
Dr. L. Eugene Cronin,
Research Professor and
Associate Director for Research
Dr. Sheldon Sommer,
Associate Professor, Geology,
University of Maryland of College Park
Dr. Chu-Fa Tsai,
Research Professor
Dr. Albert J. Pyzik
Ms. Ivis Ailin-Pyzik
Ms. Justine Welch
Mr. Blenny Chang
Mr. John Schaeffer
Mr. Mark Burke
Mr. John Paul
Mr. Jeffrey A. McKee
Mr. Raymond Rossario
Captain Martin O'Berry
and Crew
Project Coordinator
Principal Investigation,
Geochemistry
Principal Investigation,
Bioassay
Geochemistry
Geochemistry
Faculty Research Assistant
Faculty Research Assistant
Biological Aide
Biological Aide
Geochemistry
Student Assistant
Student Assistant
Master, RV AQUARIUS
The firm WAPORA, Inc., 6900 Wisconsin Avenue, Washington, D. C. ,
performed the chemical analysis for all parameters of the sediment
samples, filtered water, interstitial water, and the elutriate analysis.
H-3
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The firm Analytical Bio Chemistry Laboratories, Inc. (ABC), Columbia,
Missouri, performed the PCB analysis of the sediment samples.
The firm Micromeritics, Norcross, Georgia, Performed the particle size
and surface area analysis of the sediment samples.
H-4
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TECHNICAL REPORT DATA
(Please read Instructions on the reverse before completing)
1. REPORT NO.
EPA 440/5-77-015a
3. RECIPIENT'S ACCESSION NO.
4. TITLE AND SUBTITLE
EVALUATION OF THE PROBLEM POSED BY IN-PLACE POLLUTANTS
IN BALTIMORE HARBOR AND RECOMMENDATION OF CORRECTIVE
ACTION - Appendices
5. REPORT DATE
September 1977
6. PERFORMING ORGANIZATION CODE
7. AUTHOR(S)
8. PERFORMING ORGANIZATION REPORT NO.
9. PERFORMING ORGANIZATION NAME AND ADDRESS
Trident Engineering Associates, Inc.
48 Maryland Avenue
Annapolis, Maryland 21401
10. PROGRAM ELEMENT NO.
2 BH413
11. CONTRACT/GRANT NO.
68-01-1965
12. SPONSORING AGENCY NAME A_ND ADDRESS
Office of Water Planning and Standards
U. S. Environmental Protection Agency
401 M St., S.W.
Washington, D.C. 20460
13. TYPE OF REPORT AND PERIOD COVERED
14. SPONSORING AGENCY CODE
EPA/700/01
15. SUPPLEMENTARY NOTES
Prepared in cooperation with the Center for Environmental and Estuarine Studies,
University of Maryland, Horn Point, Cambridge, Maryland
16. ABSTRACT
This report and a companion report, EPA 440/5-77-0155, present the results of a
study of the in-place pollutants in Baltimore harbor and their effect on water
quality. This part of the report contains the appendices.
KEY WORDS AND DOCUMENT ANALYSIS
DESCRIPTORS
b.IDENTIFIERS/OPEN ENDED TERMS
COS AT I Field/Group
Environmental Research
Sediments
Water Quality
Bioassay
Baltimore harbor
Pollution
Dredging
13B
18. DISTRIBUTION STATEMEI
RELEASE TO PUBLIC
9. SECURITY CLASS (ThisReport)
UNCLASSIFIED
21. NO. OF PAGES
:0. SECURITY CLASS (Thispage)
UNCLASSIFIED
22. PRICE
EPA Form 2220-1 (9-73)
* U.S. GOVERNMENT PRINTING OFFICE 1977 0-720-117/2033
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