v-xEPA
United States
Environmental Protection
Agency
Industrial Environmental Resean
Laboratory
Cincinnati OH 45268
Research and Development
EPA-600/S7-81-082 June 1981
Project Summary
Water Pollution Potential of
Coal-Slurry Pipelines
Howard S. Peavy
Coal is expected to assume an in-
creasingly important role in meeting
America's energy needs during the
remainder of this century and, perhaps.
to become the principal source of
energy during the next. It has been
predicted that coal production will
double during the next decade, with
much of the increase coming from
low-sulfur deposits in the West. The
economics of using coal is dependent
in large measure on the economics of
transporting it, since shipment costs
can amount to as much as two-thirds
of the delivered price. Coal-slurry
pipelines have been proposed as one
economical means of transporting
coal over long distances to specific
markets.
The objective of this research project
was to characterize those contami-
nants associated with transport waters
from coal-slurry pipelines. This was
accomplished through tests using a
rotating bench-scale reactor. Tests
consisted of coal mixed with tap
water, tap water with additives, syn-
thetic saline water, and synthetic
saline water with additives. Tests
were performed for a period of 12
days each.
The results of this project indicate
that chemical interactions do occur
between water and coal under condi-
tions simulating coal-slurry pipelines.
These interactions include:
(1) A decrease in pH of approximately
two units (from approximately 8
to approximately 6). Dissolution
of metals at a pH of 6 was not
significant.
(2) An increase in mineral content
of fresh water. Alkalinity, total
dissolved solids (as indicated by
electrical conductivity), and sul-
fates each show increases. Use
of phosphorus-based chemical
additives for corrosion control
result in substantial concentra-
tions of phosphate.
(3) Turbidity remains in the water
after separation of the coal by
centrifugation. Although some
color may be present as a result
of humic acids and manganese,
colloidal particles appear to be
the main cause of turbidity.
(4) Dissolved organic carbon levels
that may be significant if reuse
(either prior to or after discharge)
requires chlorination. These or-
ganics are potential percursors
of chlorinated hydrocarbons.
This Project Summary was devel-
oped by EPA's Industrial Environmen-
tal Research Laboratory, Cincinnati,
OH, to announce key findings of the
research project that is fully docu-
mented in a separate report of the
same title (see Project Report ordering
information at back).
Coal-Slurry Operations
The technology for coal-slurry pipe-
lines is well established. As early as
1891 a patent was granted for pumping
pulverized coal in a fluid medium, and
the first slurry line operated from 1914
to 1924 in England, transporting coal
from barges in the Thames River to a
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power plant some 600 m away. To date,
two coal-slurry pipelines have been
constructed in the United States. The
first connected mines near Cadiz, Ohio,
to a power plant near Cleveland. This
line operated from 1958 to 1963 when
more favorable rail freight rates were
negotiated. The second pipeline has
been operating between Black Mesa,
Arizona, and Mohave, Nevada, since
1970. This line, 45 cm diameter and 440
km in length, carries approximately 5
million metric tons per year over terrain
considered too rough for a rail line. As
Figure 1 shows, many other coal-slurry
pipelines are presently being planned.
A coal-slurry pipeline operation is
depicted in Figure 2. Coal is ground to
the approximate consistency of table
salt and is mixed approximately 50% by
weight with water. The mixture is a
pumpable fluid with a specific gravity
slightly greater than water. A minimum
velocity of approximately 1.2 m/sec is
required to maintain all particles in
suspension. Pump stations must be
strategically located to maintain this
velocity and to overcome head loss due
to pipeline friction and elevation changes.
Potential For Pollution
Basically, coal is composed of carbo-
naceous material formed from the
compaction and subsequent partial
decay of plant remains. However, many
inherent and extraneous inorganic
substances are interspersed within the
mass of carbon molecules in bulk coal.
Inherent inorganic matter had its origin
in the vegetative matter which eventually
became coal while extraneous inorganic
matter entered the coal bed from non-
plant origin, either during or after the
coalification process.
The principal forms of extraneous
matter found in bulk coal are alumino-
silicates, sulfur compounds, carbonates
and silica. As Table 1 illustrates, various
metals are also associated with the
extraneous inorganic matter.
Many of the metals in Table 1 are
recognized as poisons and some are
known to be cumulative poisons. Al-
though most of these are virtually
insoluble in pure, metallic form, salts
and oxides of many of them are quite
soluble, as illustrated in Table 2.
Should these compounds already
exist in the coal seam, or should they be
formed due to exposure of coal to
oxygen or chlorides in the slurry water,
the potential exists for serious contami-
nation of transport water.
Miami
Existing Pipelines
Planned Pipelines
Proposed Pipelines
Pipeline Corridors Studied.
Figure 1. Existing and proposed coal-slurry pipelines. (Courtesy of Slurry
Transport Association, Washington, D.C.)
Run of Mine
Coal Stockpile*.
Cleaned Coarse
Coal Stockpile
'Slurry
Preparation
Coal
Mine
Pump Station
Dewatering
Plant
Agitated
Storage
Process/Flush Water
Slurry Storage Reservoir
Reservoir
Power Plant
Agitated
Storage
Slurry Storage Cooling
' . Water
Reservoir
Cooling
•• Water
Blow-Down
Figure 2. Coal-slurry system.
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Table 1. Trace Element Analyses of Rosebud Seam Coal
Element Analyses in parts per million (ppm) of whole coal, moisture-free basis
Maximum Average Minimum
Antimony
Arsenic
Beryllium
Cadmium
Chromium
Copper
Fluorine
Germanium
Lead
Manganese
Mercury
Nickel
Selenium
Zinc
2.55
21.30
1.91
1.510
31.20
40.3
173.0
16.35
94.0
404.5
0.61
163.5
6.62
361.0
0.61
6.02
0.44
0.129
5.37
12.5
51.0
2.64
8.8
66.1
0.20
37.3
1.29
49.6
<0.07
0.68
0.11
0.021
<0.40
4.6
4.0
30°C
5> 20°C
Very soluble
61.7 0°C
!> 0°C
i> 20°C
PbO
MnClz
HgClz
Ni C/3
Se Oz
ZnCIt
0.0017 d
72.3 4
6.9 d
64.2 «
38.4 d
432 20°C
» 25°C
J> 20°C
S> 20°C
5) 14°C
p 25°C
Slurry Water Disposal
Slurry dewatering at the pipeline
terminus recovers from 60 to 70% of the
transport water. It is generally assumed
that this water will be used in the power
production operation at the pipeline
terminus. The most common proposal is
to use it as a part of the make-up water
for cooling towers. Although cooling
tower water may have fewer quality
constraints than does water for many
other operations at power plants, highly.
mineralized waters create scaling prob-
lems. Furthermore, since cooling tower
blow-down necessitates discharge,
portions of the slurry will eventually
become an effluent, even if used for
cooling water.
Only recently have studies been
conducted to document the pollution
potential of coal slurry pipelines. In an
effort to determine the nature and
extent of chemical interaction of water
and coal in coal slurry pipelines, and to
identify the likely contaminants in the
spent slurry water, a research project
was conducted at Montana State Uni-
versity from 1977 to 1979.
Project Description
A laboratory scale reactor was con-
structed to maintain a coal-in-water
suspension for an appropriate contact
time. The apparatus consisted of a 102
cm length of 38 cm PVC pipe which
could be rotated about its longitudinal
axis. The ends were closed by 2.5 cm
aluminum plates drawn together by tie
rods. A 0.64 cm sampling port was
tapped into the center of one end plate.
A 5 cm plug was drilled and threaded
into the side of the pipe for loading
water. Baffles were installed longitudi-
nally to prevent the coal from packing
into a lump and slipping along the
bottom as the drum rotated.
The reactor sat on steel bars mounted
in pillow blocks. Torque was provided by
an electric motor attached to the drum
by a chain and sprocket arrangement.
Coal
Coal used in the experiment was from
the Western Energy mine at Colstrip,
Montana. The coal came from the
Rosebud Seam discussed previously
and was shipped in run-of-the-mine
condition to the Mineral Research
Center in Butte, Montana, for grinding.
The coal was ground by roller-crusher
and hammer-mill to the specifications
shown in Table 3.
After grinding, the coal was placed in
55 gallon drums, sealed to prevent
oxidation, and shipped to the lab in
Bozeman.
Water
Several proposals have been made
concerning sources for transport water.
In addition to the use of fresh water from
surface or relatively shallow aquifers,
suggestions have been made to import
sea water or to tap deep aquifers whose
waters are too saline for other local
uses. Experiments were run using
water which approximated the quality of
saline water in parts of the aquifer
underneath the Northern Plains coal
fields. Quality of the water is shown in
Tables 4 and 5.
Methodology
The following methodology was ad-
hered to in all the experiments. Approxi-
mately 62 kg of ground coal were placed
in the reactor and the end plates bolted
tight. The reactor was then placed on
the roller. Sufficient water (63 liters)
was added for an approximate 50-50
mixture. The reactor was turned at
approximately 10 revolutions per minute.
Nitrogen was injected to expel the sam-
ple and to prevent air entrapment. A
positive pressure of approximately 10
psi of nitrogen was maintained in the
system at all times.
Samples were taken immediately
after mixing and after six hours, 12
hours, one, two, four, eight and 12 days.
The 12-day period is sufficient to model
the detention time in the longest of the
proposed pipelines.
Analysis
Samples were analyzed for the fol-
lowing parameters:
Physical Parameters
pH
Specific conductance
Mineral Parameters
Alkalinity
Chloride
Sulfates
Metal Parameters
Arsenic
Chromium
Copper
Lead
Manganese
-------
Mercury
Nickel
Sodium
Zinc
Organic Parameters
Dissolved organic carbon
High Performance Liquid Chroma-
tography Profile (HPLC)
The pH values were measured imme-
diately after samples were drawn using
a Corning Model 12 Research pH meter.
Table 3. Grain Size of Ground Coal
Sieve No. % Weight Retained
Electrical conductivity was measured
using a Lab-line Lectro mHO-Meter
(Model MC-1, Mark IV) conductivity
meter. Samples for mineral and metal
parameters were first centrifuged at
about 2000 RPMs (approximately 81 OxG)
for about 20 minutes. The liquid was
decanted and, since it remained highly
colored in dark brown hues, wasfiltered
through a 0.45// filter. The resulting
sample was clear and contained only
dissolved species. Aliquots for metals
Sieve No.
% Weight Retained
were separated, placed in glass jars and
acidified with nitric acid.
Alkalinity and chloride analyses were
performed titrametrically while sulfates
were measured by the turbidimeter
method. Analysis for metals was per-
formed by atomic adsorption spectro-
photometry. All procedures conformed
to those outlined in Standard Methods
for the Examination of Water and
Wastewater 14ed. or Methods for Chem-
ical Analysis of Water and Waste.
Samples for analysis of dissolved
organic carbon were handled in the
following manner. Approximately 100
ml aliquots were centrifuged at 8K for
16
20
40
50
70
100
0.88
10.24
36.45
15.53
10.57
9.36
740
200
325
400
Pan
5.51
4.30
4.96
0.88
1.32
100.00
approximately 20 minutes using a
Beckmann ultracentrifuge. The water
was decanted and filtered through a
0.25/u silver metal membrane (Selas
Corporation) using a Gelman pressure
filtering apparatus. Triplicate 5 ml
aliquots were transferred to precom-
busted glass ampoules (Oceanography
Table 4. Solubility of Inorganic Chemical Parameters in Fresh Transport Water
Parameter"
pH (Units)
Electrical
Conductivity
M mhos/cm
Alkalinity
Chloride
Sulfate
Arsenic
Chromium
Copper
Lead
Manganese
Mercury"*
Nickel
Sodium
Zinc
Mix
Water
7.8
197
97
4.12
12
0.011
0.0005
0.07
0.006
<0.01
0.74
0.005
3.0
0.02
0
6.6
1190
32
4.6
700
0.014
0.0010
0.02
0.004
0.25
7.60
0.005
55
0.006
Hours
6
6.0
1190
52
4.6
860
0.014
0.0015
0.03
0.036
0.34
0.30
0.005
65
0.04
12
5.9
1220
75
4.9
866
0.014
0.0015
0.03
0.035
0.37
0.28
0.005
66
0.05
1
5.9
1430
102
5.5
866
0.021
0.0010
0.03
0.030
0.38
0.37
0.005
69
0.05
2
5.8
1430
179
4.7
866
0.013
0.0010
0.03
0.020
0.45
0.12
0.005
71
0.03
Days
4
6.0
1680
290
5.0
900
0.018
0.0010
0.03
0.033
0.53
0.22
0.005
68
0.05
8
6.3
1420
471
4.4
900
0.028
0.0010
0.03
0.035
0.63
0.52
0.005
76
0.04
12
6.2
1940
558
4.3
960
0.026
O.OO05
0.03
0.045
0.66
0.30
0.005
79
0.04
"All values in mg/l except as noted.
"•Parts per billion.
Table 5. Solubility of Inorganic Chemical Parameters in Saline Transport Water
Parameter*
pH (Units)
Electrical
Conductivity
M mhos/cm
Alkalinity
Chloride
Sulfate
Arsenic
Chromium
Copper
Lead
Manganese
Mercury**
Nickel
Sodium
Zinc
Mix
Water
8.3
52.400
96
15.200
2.080
0.012
0.093
0.48
0.038
0.04
0.78
0.010
9080
0.10
0
6.2
48.200
20
14.400
2,250
0.017
0.60
0.09
0.037
2.46
0.75
0.010
8390
0.25
Hours
6
6.0
48.700
29
13.800
2.175
0.023
0.072
0.07
0.025
3.56
0.66
0.010
7360
0.64
12
5.9
46.300
34
13.800
2.175
0.020
0.072
0.13
0.022
3.88
0.58
0.010
7520
0.02
1
6.2
49.2OO
54
13.400
2.175
0.024
0.045
0.07
0.017
3.88
0.31
0.010
7080
0.70
2
6.2
49.700
110
13.600
2.046
0.024
0.067
0.07
0.016
4.13
0.25
0.010
7450
0.81
Days
4
6.3
47.200
183
14.400
1.900
0.027
0.057
0.07
0.020
4.30
0.34
<0.010
7240
1.20
8
6.3
51.200
317
13.700
1.900
0.027
0.057
0.07
0.015
4.41
0.22
<0.010
7200
1.85
12
6.3
49.100
385
13.600
1.750
0.027
0.067
0.07
0.030
4.36
0.29
<0.010
7300
0.74
'All values in mg/l except as noted.
"Parts per billion.
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International) containing 0.24 gm po-
tassium persulfate. A Hamilton "Gas-
Tite" syringe was used for the transfer.
Six percent H3P04 (0.25 ml) was added
to each ampoule. Each sample was
purged for 8 minutes with oxygen which
had been passed over a catalyst at
500°C and sealed immediately. This
procedure was carried out on an Ocean-
ography International ampoule sealing
unit. Sealed ampoules were autoclaved
at 15 psi for about 15 hours (overnight).
Samples were then analyzed using a
Total Carbon Analyzer (Oceanography
International).
Results and Discussion
Data obtained from the fresh water
experiment are shown in Table 4 and
data from the saline water run are
displayed in Table 5. A discussion of the
parameter groups follows.
Physical Parameters
The pH of the coal-slurry system is of
importance for several reasons. Drastic
departure from neutral conditions results
in a caustic or acidic solution which may
be either corrosive or erosive to pipeline
components and to appurtenances at
the terminus. Extreme values of pH
could be significant constraints on the
reuse and/or discharge of the slurry
water.
Perhaps the most important effect of
pH in the slurry system is its effect on
the solubility of the metals and minerals
encountered in the coal. Metals and
minerals are more soluble at low pH
values while high pH values result in the
formation of hydroxide species which
precipitate.
As noted in Tables 4 and 5, pH values
for both fresh and saline water dropped
approximately two units during the
initial stages of the run. Most of the
decrease occurred immediately upon
mixing with only small fluctuations
noted thereafter. More than likely, the
pH change resulted from solution of
reduced sulfur compounds in the coal
and subsequent production of sulfuric
acid. Although pH values observed here
are not sufficiently low to solubilize
metals, care should be exercised in
extrapolating pH data to other coals
which might have a higher sulfur con-
tent, notably eastern coals.
Electrical conductivity (EC) is an
indirect measurement of total dissolved
solids (TDS). A multiplication factor of
0.65 is used to convert EC to TDS. The
esults of the EC test shown in Table 4
indicate that the TDS is increased
considerably when fresh water is used
as the transport medium. Using the
above multiplier, the TDS is seen to
increase from approximately 125 to
1250 mg/l, with most of the increase
occurring during the initial mixing
period. The TDS continues to increase
steadily, however, indicating that longer
contact times would produce higher
TDS.
The EC of the saline water is seen to
decrease with time, indicating that
precipitation is occurring or that some of
the dissolved substances are adsorbing
to the coal surfaces. Over the 12-day
run, the TDS decreases by approximately
2000 mg/l. The inorganic solids thus
removed with the coal would quite likely
cause an increase in fly ash and possibly
other problems in the furnace. Water
with this TDS would be unsuitable for
reuse and would present a pollution
problem unless discharged to the ocean
or some other salt water body.
Mineral Parameters
Mineral parameters measured in this
experiment included alkalinity, chlorides
and sulfates. Alkalinity is defined as any
substance which neutralizes acids. In
most cases, alkalinity can be attributed
to hydroxide, carbonate and bicarbonate
ions, although salts of borate, phosphate
and other material can contribute to
alkalinity. The alkalinity of a coal-slurry
system is important primarily from the
buffering capacity standpoint. If suf-
ficient alkalinity is present, significant
pH reductions due to the solution of
sulfur compounds will be avoided.
The alkalinity of both fresh water and
salt water runs dropped initially and
then increased. A logical deduction is
that acetic material, which resulted in
the initial pH drop noted earlier, also
consumed virtually all of the initial
alkalinity. After this initial reduction, the
alkalinity increased steadily and con-
sistently throughout both runs, coupled
with slight pH increases. In terms of
buffering capacity, the critical period is
indicated to be the initial mixing time. It
should be pointed out, however, that
this should not be extrapolated to high
sulfur, low alkali coals from eastern
regions.
In coal-slurry pipeline systems, the
most important characteristics of chlo-
rides would be their corrosive nature.
Chlorides in concentrations as low as
45 mg/l have been reported to have an
adverse effect on metals associated
with water-handling systems. Excessive
concentrations would be expected to
have a more pronounced effect.
As noted in Table 4, chloride concen-
trations were very low in the freshwater
and the change over the 12-day period
was insignificant. In the saline water
(Table 5), chlorides decreased by ap-
proximately 10%, or 1600 mg/l. The
chlorides could have been precipitated
as metal salts, or could have become
adsorbed to the coal particles. Chlorides
of the magnitude used in saline water
would present corrosion potential in
both the pipeline system and the power
plant using the coal. Discharge to fresh
water bodies would definitely present a
pollution potential.
Sulfate is an oxidized form of sulfur.
Sulfates in coal slurry transport water
could have several origins. Oxidation of
sulfur in the coal during mining, trans-
porting and crushing operations would
result in the dissolution of sulfates in
the slurry water. Oxidation could also
occur after mixing as a result of dissolved
oxygen in the slurry water. Formation of
sulfuric acid (H2S02) and the neutraliza-
tion of the hydrogen ions by the alkalinity
would also result in free sulfate ions.
When fresh water, initially low in
sulfates, was used as the transport
medium, sulfates increased immediately
by several hundred mg/l (Table 4) with
only a slight increase thereafter. Saline
water with a high initial concentration
of sulfates (Table 5) lost approximately
3000 mg/l after 12 days of contact in
the slurry water. In terms of water
quality, both the fresh and saline water
could present a problem if discharged to
fresh water bodies. On the other hand,
the use of fresh water results in a
washing of coal which should produce
less sulfur compounds in the stack
gases. The opposite was true when high
sulfate saline water was used.
Metal Parameters
An examination of the data in Tables 4
and 5 indicates that most of the metals
did not dissolve to any significant
extent. Arsenic, chromium, copper,
lead, mercury, nickel and zinc were all
present in measurable quantities in the
transport water, and in most cases their
concentrations decreased slightly upon
contact with the coal. The observed
concentrations of these metals were too
low to be of concern from a water quality
standpoint.
Concentrations of manganese in-
creased slowly but steadily in the fresh
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water run to approximately 0.7 mg/l
after 12 days. In the salt water run,
manganese was seen to increase rapidly,
then level off at concentrations in
excess of 4.0 mg/l. The reduced form of
manganese (Mn*+) is soluble in water
and can cause color problems at con-
centrations as low as 0.05 mg/l. In the
slurry water, manganese was probably
in the oxidized form or complexed with
other material in a particulate form,
since filtration of the slurry resulted in a
clear sample. Although it is possible
that manganese precipitate could ac-
cumulate on pipeline and power plant
appurtenances, it is doubtful that signif-
icant problems will result from concen-
trations of this level.
The increase in sodium concentra-
tions in the fresh water run is not
significant from a water quality stand-
point. It is interesting to note, however,
that sodium concentrations in the saline
water decreased by approximately 1800
mg/l. Although this decrease is not
significant from a water quality stand-
point, removal of the sodium with the
coal would result in greater quantities of
fly ash and possibly some corrosion of
furnace parts. Tests for sodium on
samples of the coal before and after
contact with the water confirmed that
the sodium remained with the coal.
Organics
Dissolved organic carbon analysis
indicated average concentrations of 24
mg/l in the fresh water run and 13 mg/l
in the salt water run. The solubility of
organic carbon is pH dependent with
saturation levels in the low 20s at pH
values between 6.0 and 7.0. Thus, the
DOC values for the fresh water run are
probably at saturation. Lesser values for
the saline water may be duetoa "salting
out," or a complexing of the organics
with some of the inorganic ions and
subsequent precipitation.
Organic analysis using High Perform-
ance Liquid Chromatography (HPLC)
indicated that the organic carbon was
probably in the form of humic and fulvic
acids. Concentrations of organic acids
of this magnitude should have little
direct threat to water quality. A potentially
serious condition could develop, how-
ever, if the spent slurry water were to be
chlorinated. Humic and fulvic acids are
percursors of haloforms which are
known carcinogens. Since it is a common
practice to chlorinate cooling tower
water to control biological growths, use
of the spent slurry water for make-up
water to the cooling tower would almost
certainly result in haloforms. Blow-
down of the cooling water could result
in discharge of these carcinogenic com-
pounds.
Summary and Conclusions
Coal-slurry pipelines have proven to
be a reliable and economical means of
transporting coal over long distances to
specific markets. At the pipeline ter-
minus, large volumes of water must be
separated from the coal. Although reuse
of this water, probably as cooling water,
in the power plant operation is antici-
pated, portions of the transport water
are likely to be discharged ultimately.
The quality of the spent slurry water is
therefore of importance.
Experiments at Montana State Uni-
versity which modeled coal-slurry sys-
tems indicated that some chemical
interaction between coal and transport
water will occur in the pipeline. Fresh
water will experience an increase in
total dissolved solids while the TDS of
saline water will decrease. Analysis of
coal samples prior to and after the
experiment indicated that the material
lost from the water remained on or with
the coal.
The pH of the slurry tested dropped by
approximately two units almost instan-
taneously and then stabilized. Alkalinity
initially dropped and then increased
significantly. Apparently acetic com-
pounds in the coal dissolved quickly,
neutralizing the alkalinity. Whether the
dissolution of the acetic material ceased,
or alkalinity from the dissolution of
alkali material was more than sufficient
to neutralize the acid is not known. The
pH values remained sufficiently high
(around pH 6.0) that significant dis-
solution of metals did not occur.
Analysis for organics indicated aver-
age dissolved organic carbon concen-
trations of 24 mg/l in fresh water and
13 mg/l in saline water. These values
are close to saturation concentrations at
pH 6 and the DOC was found to be
primarily humic and fulvic acids.
Conclusions can be drawn that saline
water is not a satisfactory transport
medium since it increases the mineral
content of the coal which would produce
greater quantities of fly ash and exacer-
bate corrosion of furnace components.
Use of the saline water in the power
plant operations would be limited and
discharge to fresh water bodies would
probably be prohibited.
Solubilization of minerals and organics
in initially fresh transport water will
limit its usefulness in the power plant
and will probably necessitate treatment
prior to re-use and/or discharge. Removal
of the dissolved organics, or use of
algalcides other than chlorine will be
necessary to prevent formation of halo-
form compounds.
6
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Howard S. Peavy is with the Department of Civil Engineering and Engineering
Mechanics, Montana State University, Bozeman, MT 59715.
Jonathan G. Herrman is the EPA Project Officer (see below}.
The complete report, entitled "Water Pollution Potential of Coal-Slurry Pipe-
lines." (Order No. PB 81-187 221; Cost: $9.50, subject to change) will be
available only from:
National Technical Information Service
5285 Port Royal Road
Springfield, VA 22161
Telephone: 703-487-4650
The EPA Project Officer can be contacted at:
Industrial Environmental Research Laboratory
U.S. Environmental Protection Agency
Cincinnati, OH 45268
4 US OOVEBNMENT PRINTING OFFICE 1M1-757-012/7144
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United States
Environmental Protection
Agency
Center for Environmental Research
Information
Cincinnati OH 45268
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Fees Paid
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Agency
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Penalty for Private Use $300
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