United States
Environmental Protection
Agency
Effluent Guidelines Division
WH-552
Washington DC 20460
EPA-440-1-82'059
June 1932
Water and Waste Management
v>EPA Report to Congre^w
The Effects of Discharges
from Limestone Quarries
on Water Quality
and Aquatic Biota
-------
THE EFFECTS OF DISCHARGES
FROM LIMESTONE QUARRIES ON
WATER QUALITY AND AQUATIC BIOTA
A REPORT TO THE
CONGRESS OF THE UNITED STATES
Prepared by:
U. S. Environmental Protection Agency
Effluent Guidelines Division
Washington, D. C.
June 1982
-------
NOTICE
This report has been reviewed by the Effluent Guidelines Division, Office of Water,
U.S. Environmental Protection Agency and approved for publication. Mention of
trade names or commercial products does not constitute endorsement or recommendation
for use.
-------
UNITED STATES ENVIRONMENTAL. PROTECTION AGENCY
WASHINGTON, D C 20460
JUN 15 B82
THE ADMINISTRATOR
Honorable George Bush
President of the Senate
Washington, D. C, 20510
Dear Mr. President:
I am pleased to submit the enclosed report entitled "The Effects of
Discharges from Limestone Quarries on Water Quality and Aquatic Biota."
This report is being forwarded to you in response to a request from the
Senate Committee on Environment and Public Works during its.discussion
on the Clean Water Act Amendments of 1977. (Senate Report No. 95-370
page 83).
This report presents the results of extensive data collection efforts
that included literature searches, sampling for biological effects, and
water quality sampling and analysis. Included in the report is an evalu-
ation of wastewater treatment technology and a cost analysis.
The results of this study indicate that wastewater which has been
treated to remove suspended solids causes minimal adverse effects on
ambient water quality. However, untreated wastewater from this industry,
in spite of the beneficial effects due to its chemical composition, can
cause substantial adverse physical effects which are due to siltation.
I hope that this report will be useful to you in development of any
future policy or legislation affecting the limestone mining industry. I
appreciate this opportunity to be of service to you.
Sincerely yours,
Anne M. Gorsuch
Enclosure
-------
•0T
UNITED STATES ENVIRONMENTAL PROTECTION AGENCY
WASHINGTON, DC. 20460
JUN 15 1982
THE ADMINISTRATOR
Honorable Thomas P. O'Neill, Jr.
Speaker of the House of Representatives
Washington, D.C. 20515
Dear Mr. Speaker:
I am pleased to submit the enclosed report entitled "The Effects of
Discharges from Limestone Quarries on Water Quality and Aquatic Biota."
This report is being forwarded to you in response to a request from the
House Committee on Public Works and Transportation during its discussion
on the Clean Water Act Amendments of 1977. {Congressional Record, H12938,
December 15, 1977).
This report presents the results of extensive data collection efforts
that included literature searches, sampling for biological effects, and
water quality sampling and analysis. Included in the report is an evalu-
ation of wastewater treatment technology and a cost analysis.
The results of this study indicate that wastewater which has been
treated to remove suspended solids causes minimal adverse effects on
ambient water quality. However, untreated wastewater from this industry,
in spite of the beneficial effects due to its chemical composition, can
cause substantial adverse physical effects which are due to siltation.
I hope that this report will be useful to you in development of any
future policy or legislation affecting the limestone mining industry. I
appreciate this opportunity to be of service to you.
Sincerely yours
Anne M. Gorsuch
Enclosure
-------
TABLE OF CONTENTS
Page
1.0 SUMMARY 1-1
2.0 CONCLUSIONS ...2-1
3.0 INTRODUCTION. .3-1
4.0 DESCRIPTION OF SAMPLING AND ANALYTICAL PROCEDURES ...4-1
4.1 Water Quality Sampling ........4-1
4.1.1 Sample Collection .....4-1
4.1.2 Sample Preparation ......4-2
4.2 Biological Sampling Procedures 4-3
4.3 Water Quality Analyses Procedures.... 4-4
5.0 DESCRIPTION OF SITES VISITED 5-1
5.1 Introduction. .5-1
5.2 Site Descriptions...... ......5-6
5.3 Self-Monitoring Historical Data 5-40
6.0 RESULTS OF SAMPLE ANALYSES.. ....6-1
6.1 Water Quality Analyses. 6-1
6.2 Ecological Analyses 6-17
6.2.1 Ft. Calhoun Stone Company 6-17
6.2.2 River City Products.... .6-22
6.2.3 The Stone Man, Inc..... 6-22
6.2.4 Southern Stone Co 6-26
6.2.5 Flintkote Stone Products, 13
February, 1980 .6 -28
6.2.6 Oldham Stone Co 6-30
6.2.7 Kentucky Stone Company .6-34
6.2.8 France Stone Company, Monroe,
Michigan .6-34
Preceding page blank
vii
-------
TABLE OF CONTENTS
(Continued)
Page
6.2.9 France Stone Company, Bloomville,
Ohio 6-37
6.2.10 Flintkote Stone Products, 24 July
1980 6-37
7 . 0 EFFECTS OF DISCHARGE 7-1
7 .1 Water Quality Effects 7-1
7.1.1 Suspended Solids and Turbidity 7-2
7.1.2 Dissolved Solids 7-9
7.1.3 Hardness 7-12
7.1.4 Silica 7-14
7.1.5 pH 7-15
7.1.6 Heavy Metals 7-16
7.1.7 Asbestos.. 7-19
7.2 Ecological Effects of Limestone Quarry
Effluent 7-21
7.2.1 Effects of Limestone Quarry Ef-
fX\j.6nts on Fi.sli7™25
7.2.1.1 Effects on Adult Fish 7-27
7.2.1.2 Effects on Fish Reproduc-
tion Behavior and Success.. 7-31
7.2.2 The Effects of Limestone Quarry
Effluents on Benthic Communities.... 7-34
7.2.3 Plankton, Periphyton, Macrophytes
and Attached Algae. 7-35
8 . 0 TREATMENT TECHNOLOGIES 8-1
8.1 Description of Treatment Technologies 8-1
8.1.1 Settling Ponds 8-1
viii
-------
TABLE OF CONTENTS
(Continued)
Page
8.1.2 Flocculation 8-2
8.1.3 Clarifiers 8-2
8.1.4 Filtration 8-3
8.1.5 Water Management Practices.......... 8-3
8.2 Treatment Cost 8-4
9.0 REFERENCES 9-1
Preceding page blank
X
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ACKNOWLEDGEMENTS
This document was developed from reports prepared by Radian
Corporation. The staff at Radian Corporation, under the supervision of
Mike McCloskey included Mike Hoban, Chris Lippe and Nancy Pacharzina.
the staff is greatly acknowledged for their valuable efforts in field
investigation, water sampling, biological sampling, and preparation of
the report.
Obviously all the quarry owners and operators provided the
vital input to the study, the quarries for field sampling. The authors
appreciate the efforts of Jess Wright of Fort Calhoun Stone Co.,
Tom Scott of River Products Co., Rick Cole of Flinkote Stone Products,
Mike Staudohar of France Stone Co., Ernie Riggs of Southern Stone,
Robert Blaker of Oldham County Stone Co., Don Connel1 of The Stone Man,
Inc., and Jay,Brown of Kentucky Stone Co.
The National Crushed Stone Association, Portland Cement
Association, and National Limestone Institute provided consultation
on treatment cost data and possible quarry visit sites.
Project Officer for this study was Ron Kirby, U.S. Environ-
mental Protection Agency, Effluent Guidelines Division.
xi
-------
1.0 SUMMARY
This report documents the procedures, analysis results, and
conclusions of a study to identify the effects of limestone quarrying
and processing operations on water quality and aquatic biota.
Data was gathered both from the literature and by sampling
various process streams and discharge receiving streams at nine dif-
ferent limestone quarries. Published data was gathered on the effects
of constituents typically present in discharges from limestone oper-
ations on water quality and aquatic biota. Field sampling was
conducted at quarries in Nebraska, Iowa, Michigan, Ohio, Kentucky,
Tennessee, Alabama, and Maryland. The sampling was done to confirm
the levels of total suspended solids, dissolved solids, hardness, pH,
silica, turbidity, lead, mercury, nickel,, chromium, cadmium, selenium,
zinc, iron and asbestos in limestone operation process waters and dis-
charges. In addition, the receiving streams were analyzed by biologists
for effects on aquatic biota of limestone operation discharges.
Water samples were taken at various points within the
limestone facilities to assess the effectiveness of treatment methods
used.
It was found that:
o wastewater treatment by use of sedimentation ponds
which are standard practice for this industry remove
a significant portion of the pollutants in the untreated
process water and mine water when properly operated,
o treated effluents have a minimum impact on water quality
and aquatic biota,
1-1
-------
washwater discharged without treatment could have
significant effect on water quality and aquatic
biota,
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2.0 CONCLUSIONS
The following conclusions can be drawn from this study:
o Simple wastewater treatment techniques (I.e. sedimentation
ponds) are very effective 1n reducing levels of pollutants
1n effluent discharges from limestone quarrying and processing
operations. Most operations employ this method of treatment.
o Levels of total suspended solids (TSS) In treated effluents
should cause 11 ttle Impact to water quality or aquatic biota.
o Levels of TSS In untreated washwater could adversely affect
water users and most forms of aquatic biota If discharged
without treatment.
o Treatment for pH control of effluent discharges from limestone
quarries Is seldom, 1f ever, required to meet water quality
standards.
o Trace elements (lead, mercury, nickel, chromium, cadmium,
selenium, zinc, and Iron) are present at low or below
detectable levels In effluent discharges from limestone
operations. These levels are contained primarily In the
sol Ids, Treatment to remove suspended solids will also
remove some metals.
o Asbestos fibers at lov/ or natural background levels are
found in discharges from some limestone operations. Treat-
ment to remove suspended solids will also be a control and
remove some asbestos.
o Modifications to operation management practices at some
quarries could reduce Impacts on receiving streams.
In some cases the TSS
-------
level at the confluence of effluent stream
and the receiving stream is an order of mag-
nitude higher than the TSS level of the
treated effluent,
• No limestone operations were identified that
were forced to close because of Increased
cost of operation resulting from regulatory
compliance during the time effluent regula-
tions were in effect.
2-2
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3.0 INTRODUCTION AND BACKGROUND
The Environmental Protection Agency promulgated final effluent
guidelines for the crushed stone subcategory within the mining and mineral
processing industry on July 12, 1977 (FR, July 12, 1977, Vol. 42, No. 133).
Limestone quarrying and processing operations were included in this
subcategory. Following the promulgation of these guidelines,
representatives of the crushed stone industry challenged the guidelines.
The Fourth Circuit Court of Appeals remanded the guidelines on June 18,
1979. (National Crushed Stone Association v. EPA, 13 ERC 1277).
In 1977, Congress during its discussion on the Clean Water Act Amendments
requested that EPA conduct a study to consider the effect of
limestone quarrying operations on water quality. Radian Corporation
was chosen to conduct the study, and work was begun in the Fall of 1979.
The study consisted of a literature survey and field sampling to
gather data on the types and quantities of constituents present in
limestone discharges, and their effects on water quality and aquatic
biota.
Ten field surveys were planned and conducted at limestone
operations that provided a random geographical distribution among
limestone producing areas. It was desired that these visits be made
to medium to large size (production) plants with and without limestone
washing operations. These operations needed to have distinct discharges
to reasonably sized receiving streams. Identification of such
facilities was more difficult than anticipated. Table 3-1 presents
a summary of quarries contacted, but not visited, and the reason for
their not being selected for field surveys. Figure 3-1 shows the
locations of sites selected in this study (one site was visited
twice). Figure 3-2 shows the distribution of limestone quarries across
the nation. The exact locations and names of the selected quarries are
given in Section 5.0.
3-1
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TABLE 3-1. LIST OF CONTACTED QUARRIES NOT SELECTED FOR FIELD SURVEYS
Quarries/Companies Contacted
Location
Individuals Contacted
(Provided Information on
thla number of quarries
and their processes)
Connects
CO
I
to
Sterling Crushed Stone Co.
Trinity Quarries Co.
Bulllt Stone Co.
Kentucky Stone Co.
Hoover, Inc.
Anchor Stone Co.
Texas Crushed Stone
Loneatar Industries
Parker Brothers
Dolese Brothers-
Hemphill Bros*, Inc.
Mulzer Ciushed Stone
Raid Co.
nlaml, Florida
Decatur, Alabama
Shepherdsvll1e, Kentucky
Louisville, Kentucky
Nashville, Tennessee
Tulsa, Oklahoma
Austin, Texas
Throughout Texas
New Braunfela, Texas
Oklahoma City, Oklahoma
Seattle, Washington
Tell City, Indiana
Burllneton, Iova
Arthur Larson
O'lO)
Bobby Lee Watera
Jay Brown
(M5)
(*5)
(MO)
Virgil Smith
(MO)
Wiley Hemphill
Phillip Bakomb
(3)
Ron Garrison
(5)
They had no discharge to a waterway. Mr. Larson Indicated that to
his knowledge, no one In South Florida discharged to a waterway.
This la due to high seepage rates through sedimentation pond bottoms.
They had only a pit discharge after heavy rain.
Does not discharge.
We did vlalt one of their quarries, but they had 14 more that either
had 100Z recycle or only had intermittent pit discharges.
Recycle with no discharge.
No discharge.
No discharge.
No dlacharge.
No dlacharge.
Recycle at numerous plants.
Their washing operation discharges to the Pacific Ocean. They have
"the lion's share" of washed limestone In the Northwest.
They had no washing operation and discharged to the Ohio River.
Closed systems
(Continued)
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TABLE 3-1. LIST OF CONTACTED QUARRIES NOT SELECTED FOR FIELD SURVEYS (Continued)
Quarries/Companies Contacted
Location
Individuals Contacted
(Provided Information on
this number of quarries
and their processes)
Consents
U>
I
U>
City Quarries
Kaser Co.
General Crushed Stone
General Crushed Stone
Dolclto Quarry Co.
Vulcan Materials
Martin-Marietta
Anerlcan Aggregates
Castle Concrete Co.
General Dynamics
Utah Calcium Co., Inc.
Columbia. Missouri
Des Moines, Iowa
Glenn Hills, Pennsylvania
Dovnlngtovn
Birmingham, Alabama
Birmingham, Alabama
Raleigh, North Carolina
(Eastern Division)
lowa
(Central Division)
Indiana and Ohio
Colorado
Colorado
Utah
Ray Bohlken
Jerry Noosebaua
Vern Schneider
(MO)
Vern Schneider
(MO)
Walter Frldley
(>10)
Bill Ross
(>10)
Tom Sellers
(>10)
Bill Hole
(4)
Charlie Bacley
(3)
Mr. Hartman
(3)
Unknown
No discrete discharge, only seepage.
Very small, Intermittent washing operation.
Pit discharge (closed system).
Pit discharge.
Closed cycle washing operation.
There are no plants meeting criteria of a discharge of process
water to a small stream.
There are no plants with washing discharges, only pit dewatering,
recycle, or no discharge.
rrobably 99Z of plants are closed systems. Cuulu uol find one
which discharged process water.
All but one are pit dewatering only. One Is a washing discharge
into large lakes and then the Sclota River (too large).
No dlacharge, water is reused.
No discharge, water shortage
"Mine is In the desert"; no water.
(Continued)
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TABLE 3-1. LIST OF CONTACTED QUARRIES NOT SELECTED FOR FIELD SURVEYS (Continued)
Quarries/Companies Contacted Location
Individuals Contacted
(Provided Indorsation on
this number of quarries
and their processes)
Comments
I
Guernsey Stone Co.
Wyoming Construction Co.
Kaiser Cement and Gypsum
Corp.
Austin White Lime
National Lime Association,
Texas Division
McDonald Brothers
Gifford-Hill
N. R. Haram Quarries
Fogle Quarries
Midwest Minerals
Reno Construction
Llnwood Stone Products
Halquist Stone
Waukesha Lime & Stone
Guernsey, Wyoming
Laramie, Wyoming
Oakland, California
Austin, Texas
Waco, Texas
San Antonio, Texas
New Braunfels, Texaa
Herrlngton, Kansas
Ottowa, Kansas
Glrard, Kansas
Overland Park, Kansas
Davenport, Iowa
Sussex, Wisconsin
Waukesha, Wisconsin
Leonard Wolfe
Unknown, 1 quarry
John Wlmberly
Sandra Claro
Charlie Baxter
Larry Irvln
Mr. Ivey
Clayton Strom
Unknown
Richard Atklsman
K. 0. Thomas
Gaye Krewer
Perry Halqulst
Mr. Dewey
Water Is pumped out of a river, used for dust control. There Is no
discharge.
The operation Is a hillside quarry, no crushing, no water. This
contact knew of no wet operations In the area. Most limestone In
area Is In hillside outcrops so there Is no ground water encoun-
tered.
They had no water. There are probably no quarries that discharge.
They had no discharge.
Knew of no quarries or plants discharging, only recycle.
No discharge.
No discharge.
No washing.
Aggregate, no washing.
No washing.
No discharge, wash water Is reused.
Discharges to the Mississippi River.
Declined to participate In study.
Declined to participate in study.
-------
Figure 3-1, Locations of Sites Visited
-------
LO
I
CT»
High Limestone Quarry Concentration
III Moderate Limestone Quarry Concentration
n Low Limestone Quarry Concentration
1
in
5
x
Figure 3-2. Limestone Quarry Distribution
-------
Surveys were not made to quarries in areas with dry
climate, such as the southwest. Quarries in such areas of the
country tend to recycle their water, thus having no discharge.
Quarries in Florida typically do not: discharge because of prohi-
bition by a state law and because the high infiltration rates of
most sedimentation pond bottoms leaves no excess water to dis-
charge. The quarries located in the western and mountain states
typically do not use a wet process in their process operations.
As Figure 3-1 indicates, the sites selected represent a reason-
able distribution among the quarries available for sampling.
3-7
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4.0 DESCRIPTION OF SAMPLING PROCEDURES
Two distinct types of samples were collected at each site: samples
related to the quality of untreated and treated waters and samples for the
assessment of impact on aquatic biota and water quality of the receiving
stream.
4.1 Mater Quality
Sample collection points were identified during a tour of each
quarry provided by quarry personnel. Sample points generally included:
simp discharges, wash water supply, untreated wash wastewater, and treated
wash wastewater.
The basic procedure at each station consisted of compositing
four samples collected at one hour Intervals, and then filling containers
with the sample, preserving, and labeling. The procedures are described
below in detail.
4.1.1 Sample Collection
At each sample point within a quarry, four water samples were
collected at one hour Intervals and composited. Hourly samples were 1.5
liters each and were composited in eight (8) liter polyethylene containers.
Since the volume of flow upstream of each sample point was controlled by a
pump, flows remained relatively constant at each sample point during the
sample period. Therefore, flow proportioning of hourly samples was not
necessary.
At each station, a grab sample to be analyzed for asbestos was
collected in specially cleaned, narrow mouth, one liter polyethylene
bottles provided by the Sample Control Center at EPA. The bottle was
rinsed three times in the source, filled, and sealed.
4-1
-------
4.1.2 Sample Preparation
When four (4) hourly samples were collected and composited, the
following procedures were followed for preparing samples to be analyzed
for physical parameters (total sol Ids, total dissolved solids, total sus-
pended solids, hardness, silica, turbidity, and pH), total metals, and
dissolved metals and asbestos.
Physical Parameters
A 500 ml polyethylene container was filled with the composited
sample for the analyses of total solids, total suspended solids, total
dissolved solids, hardness, silica, turbidity, and pH. The container
was labeled (date, location, station and parameters) and put on ice.
Total Metals
Two one liters polyethylene containers were filled with the
composited sample for the analyses of total concentrations of lead,
mercury, nickel, chromium, cadmium, selenium, zinc, and acid, labeled,
and put on ice. One liter was analyzed using an atomic absorption
spectrometer, the other an inductively coupled plasma optical emission
spectrometer. (ICP)
Dissolved Metals
Two liters of the composited sample were filtered through an
0.45 micron Mil 1 pore filter using a vacuum pump and a Mill pore filtering
beaker and flask. The filtrate was poured into two one liter polyethylene
containers and four milliliters of nitric acid were added for preserva-
tion. The containers were labeled and placed on ice. These samples were
4-2
-------
to be analyzed for the dissolved portion of lead, mercury, nickel, chromium,
cadmium, selenium, zinc, and iron. One liter was analyzed using an
atomic absorption spectrometer, the other an inductively coupled plasma
optical emission spectrometer.
Asbestos
One milliliter of 2.71% mercuric chloride solution was added
to the sample and the pH of the sample was measured using hydrion paper.
The bottle was then labeled with a Sample Control Center Traffic Report
sample number and placed in the shipping container provided.
4.2 Biological Sampling Procedures
The receiving streams into which the limestone quarries discharged
effluents were assessed for water quality parameters such as depth,
temperature, pH, conductivity, dissolved oxygen, and oxidation-reduction
potential. Biotic samples were taken in the receiving stream and analyzed
for benthic invertebrates, periphyton, attached algae, plankton, and
nekton.
Receiving Stream Water Quality
The water quality of the receiving stream was analyzed with a
Hydro lab 8000®. This instrument is capable of analyzing depth, pH,
conductivity, temperature, dissolved oxygen, and oxidation-reduction
potential. Sites above and below the quarry outfalls were monitored.
4-3
-------
4.3 Water Quality Analyses Procedures
The metal parameters for which analyses were performed included
total and dissolved lead, mercury, nickel, chromium, cadmium, selenium,
zinc, and iron. Analyses for total solids, total dissolved solids,
total suspended solids, hardness silica, turbidity, and pH were also
performed. Methods of analysis are cited in "Guidelines Establishing
Test Procedures for the Analyses of Pollutants", (Federal Register 40
CFR Part 136). All samples were analyzed for the presence of metals by
two methods using inductively coupled plasma optical emission spectroscopy
(ICP) and atomic adsorption spectroscopy (AA). The analyses for mercury
and selenium were by AA only.
Analyses for ICP were performed using methods and techniques
described in "Methods for Chemical Analyses of Water and Wastes", pub-
lished by EPA Environmental Monitoring and Support Laboratory, Cincinnati,
Ohio, third edition, March 1979. The method for analyses by ICP is a
proposed method cited in the Federal Register, vol. 44, no. 233, December
3, 1979, pp. 69559.
Asbestos analyses were performed using the method outlined in
"Preliminary Interim Procedure for Fibrous Asbestos," (published by EPA,
Athens, GA). Analyses for total fibers and chrysotile were completed.
4-4
-------
Benthic Invertebrates
The benthic invertebrates were sampled with a Modified
Ekman dredge. The collected sediments were sieved in the field
through a Wildco #119 sieve. All benthic samples were preserved
in 5 percent hexanine buffered formalin for transport to the
laboratory. In the laboratory the samples were rinsed in
ethanol/rose bengal and the invertebrates sorted. Sorted
invertebrates were stored in ethanol. Identifications of
invertebrates were based on Pennak, 1979; Holsenger, 1972;
Burch, 1972; Klemm, 1972, Williams, 1972; Hobbs, 1972, Burch,
1973; Foster, 1972, Ferris, 1972; Kenk, 1972; Brown, 1972; and
Needham and Needham, 1962,
Attached Algae and Plankton
Macroscopic attached algae were removed from the sub-
strate by hand and preserved in 27„ hexamine buffered. Plankton
were collected with a 35 ym mesh phytoplankton net (Biocontrol
Corporation, Pt. Sanilac, Michigan). Plankton samples were pre-
served in 1 percent hexmine buffered formalin and transported
to the laboratory for identification. Identifications were based
on Bourelly, 1966, 1968, 1970; Chapman, 1962; Patrick and Reimer,
1966; Smith, 1951; Prescott, 1970; and Eyles et al., 1944.
Nekton
Nekton were sampled with minnow seines or throw nets.
Samples were preserved in 5 percent formalin for transport to the
laboratory. Samples were field identified when appropriate.
Identifications were based on Needham and Needham, 1962; Harlan
et al., 1951; Eddy et al., 1960; Douglas, 1974; McClane, 1978;
and Trautman, 1957.
4-5
-------
5.0 DESCRIPTION OF SITES VISITED
5.1 Introduction
In order to assess the ecological impacts of limestone
operation effluents upon receiving stream biota, the following
criteria were used in site selection:
• quarry operations selected must discharge ef-
fluents rather than use closed cycle systems;
• associated receiving waters should be peren-
nial streams or lakes, small enough (physical
size and flow quantities) that biological
sampling is feasible;
• receiving waters should be relative free
from other sources of pollution; and
• selected quarries should be in areas
representative of the various ecoregions
of the United States.
A total of ten sampling trips were made to nine dif-
ferent facilities. Table 5-1 summarizes the locations, dates,
and sample points for this sampling program. Table 5-2 lists
the sites by ecoregions, and Figure 5-1 shows that the sites
visited provide a good distribution in the ecoregions where
quarries meeting the listed criteria exist. The remainder of
this section will provide a more detailed description of each
site visited. In addition, historical self-monitoring data will
be summarized for all facilities.
5-1
-------
TABLE 5-1. SUMMARY OF SITES VISITED AND SAMPLE POINTS
Quarry
Location
Date
Sampled
Sample
Point*
Sample Point Description
Ft. Calhoun Stone Ft. Calhoun, Nebraska 12/18/79
Co.
River Products,
Inc.
Stone Man, Inc.
Iowa City, Iowa
Southern Stone Co. Birmingham, Alabama
Flintkote Stone
Products Co.
12/19/79
Chattanooga, Tennessee 1/24/80
1/25/80
Cockeysville, Maryland 2/13-14/80
and
7/24-25/80
1 Pit dewatering discharge
2 Pit dewatering discharge
1 Pit dewatering discharge
1 Pit dewatering discharge
2 Sedimentation pond discharge
1 Pit dewatering discharge
2 Washing water supply
3 Untreated washing wastewater
4 Sedimentation pond effluent
5 Discharge point of lake
1 Untreated washing wastewater
2 Sedimentation pond effluent
(Continued)
-------
TABLE 5-1. SUMMARY OF SITES VISITED AND SAMPLE POINTS (Continued)
Quarry
Location
Date
Sampled
Sample
Point*
Sample Point Description
3
Untreated frother flotation
effluent
4
Frother sedimentation pond
effluent
5
Calcite mine discharge
6
Pit dewatering discharge
Oldham County
Stone Co.
Louisville, Kentucky
2/28/80
1
Pit dewatering discharge
Kentucky Stone Co.
Elkton, Kentucky
o/on /on
L-t t- y t uu
1
D4 f rA ATjfl 4nrv (A 4 e? r» V» o T" rr e*
X XU UUAdUk.1 4-ltg U
France Stone Co.,
Monroe Quarry
Monroe, Michigan
5/13/80
1
2
3
Pit dewatering and wash water
supply
Untreated stone sand washing
wastewater
Untreated crushed stone washing
wastewater
France Stone Co.,
Bloomville Quarry
Bloomville, Ohio
7/23/80
1
Pit dewatering discharge
*Sample point numbers correspond to sample location shown on quarry process diagrams in Section 5.2.
-------
TABLE 5-2. QUARRIES LISTED BY ECOREGION
Ecoregion
Southeastern Mixed Forest-
Outer Coastal Plain Forest
Quarry
Southern Stone Co.
Birmingham, Alabama
Flintkote Stone Products Co.
Cockeysville, Maryland
Eastern Deciduous Forest
The Stone Man, Inc.
Chattanooga, Tennessee
Kentucky Stone Co.
Hopkinsville, Kentucky
Oldham County Stone
Louisville, Kentucky
Monroe Stone Plant
Monroe, Michigan
France Stone Co.
Bloomville, Ohio
Tallgrass Prairie
Ft. Calhoun Stone Co.
Ft. Calhoun, Nebraska
River Products, Inc.
Iowa City, Iowa
5-4
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DOMAIN BOUNDARY
DIVISION BOUNDARY
1
in
»
o
5
x
I PACIFIC
I STEPPE I SHORT GRASS PRAIRIE IINTERMOUNTAIN
Ba tall brass i prairie / parkland / brushland
HB> LAURENTIAN MIXED FOREST
He EASTERN DECIDUOUS FOREST
IDd SOUTHEASTERN MIXED FOREST (OUTER COASTAL PLAIN FOREST
HE TROPICAL SAVANNAH
A QUARRY LOCATION
Figure 5-1. Limestone Quarries by Ecoregion
-------
No quarries were sampled in the steppe/shortgrass
prairie/intermountain, tropical savannah, Pacific, or northern-
coniferous forest ecoregions. The steppe/shortgrass prairie/
intermountain ecoregion limestone quarry operations are dry op-
erations with no receiving streams. The tropical savannah and
Pacific and northern coniferous forest ecoregions lack extensive
limestone deposits and associated quarry activities.
5.2 Site Descriptions
Ft. Calhoun Stone Company
The Ft. Calhoun Stone Company has two limestone quar-
ries in the area of Ft. Calhoun, Nebraska. The larger of the
two, producing about 400,000 tons per year, was visited on De-
cember 17 and 18, 1979. A diagram of the quarry process and
discharge points is presented as Figure 5-2. This quarry con-
sists of two pits (numbers 002 and 004) and two pit sumps, a
crushing plant, and a washing plant with a sedimentation pond
(100 percent recycle).
Pit number 004 is currently being mined, while pit
number 002 is inactive. However, both pits were being dewat-
ered by pumping during our visits. Pit 002 (1) and pit 004 (2)
were both sampled on December 18. Pit 004 (sample point 2) dis-
charges to an intermittent stream (Figure 5-3) approximately 100
feet from the Missouri River. The discharge point is approxi-
mately 6 feet above the ditch (Figure 5-4). By the time the ef-
fluent reaches the river, it has high turbidity (Figure 5-5, ef-
fluent on right, river water on left) due to the sediment load
picked up in the ditch. Pit 002 (sample point 1) discharges to
a manmade ditch (Figure 5-6) which also drains about 100 feet to
the Missouri River. The discharge is at ground level. The only
5-6
-------
INACTIVE
STONE
SUMP
SUMP
1
I"
!u
Q
5
z
m
i
(9
Z
oc
Ul
H
<
Ui
a
CRUS
»HING
WASHING
PRODUCT
PRODUCT
(9
z
oc
Ui
I-
<
Ui
a
WATER '
SUPPLY
RECYCLE
SEDIMENTATION
POND
MISSOURI RIVER
Figure 5-2. Process Diagram, Ft. Calhoun Stone Company, Ft. Calhoun, Nebraska
-------
Figure 5-3, Ft. Calhoun Stone Co., Discharge
Ditch of Pit 004
Figure 5-4. Ft. Calhoun Stone Co., Pit 004
Discharge
5-3
-------
Figure 5-5.
Ft. Calhoun Stone Co., Mixing Zone
of Pit Discharge 004 Ditch and
Missouri River (Effluent on right)
pc. oainoun stone ix>. , nc
Discharge 002
.figure j-o
5-9
-------
flow in this ditch is the occasional discharge from Pit 002,
The effluent is less turbid than the river (Figure 5-7, effluent
on right, river water on left).
The washing plant had been shut down for the winter.
When in operation, the plant recycles water to and from a sedi-
mentation pond. Due to evaporation and seepage, additional
water is occasionally pumped xnto the pond from the Missouri.
River, but there is no discharge from the pond.
D "| * jr/j ¦*" p-*¦» 4* q T p
jLv JLt V Vp. *1» Xi V-/ \i> *¦§¦ j JL.11«
River Products, Inc. operates the Conk1in Quarry located
in Iowa City, Iowa. Conklin Quarry has been in operation since
1920, and a new plant was constructed at the quarry in 1970. The
crushing plant produces a variety of limestone products including
rip-rap, roadstone, asphaltic and concrete aggregate, and agricul-
tural lime. In 1979, this quarry produced 642,000 tons of stone.
A diagram of the quarry operation and discharges is pre-
sented as Figure 5-8. The only discharge from Conklin Quarry at
the time of sampling was a discharge from the pit sump to the
Iowa River. The pit stamp discharge was sampled at sample point
(1) on December 19, 1979. The pit water is made-up of ground-
water seepage, storm runoff, and percolation from the wastewater
sedimentation pond which is separated from the pit sump by a gra-
vel dam. The water supply for the stone washing plant is from the
Iowa River and discharge is directly to the river (Figure 5-9).
The Stone Man, Inc.
The Rossville Quarry of the Stone Han, Inc. is located
in Chattanooga, Tennessee. This quarry, which produces about
500,000 tons per year of crushed stone, was visited on January 24,
1980.
5-10
-------
Figure 5-7
ft. Calhoun Stone Co., Mixing
Zone of Pit Discharge 002 Ditch
sourl River (Effluent on
11
-------
Lr.
1
M
SEDIMENTATION
POND
QUARRY
PIT
GRAVEL
DAM
^ PRODUCT
^ PRODUCT
O
WATER
SUPPLY
IOWA RIVER
WASHING
CRUSHING
1
i"
a
2
»
X
Figure 5-8. Process Diagram, River Products, Inc., Iowa City, Iowa
-------
Figure 5-9. River City Products. Discharge
into Iowa River
CI O
to# Am Hio#
-------
As illustrated in Figure 5-10, the Rossville plant con-
sists of a ten acre pit, a pit sump, and one crushing plant with
a washing operation available when needed. A settling pond on
the site (created from an inactive pit) receives the pit dewater-
ing discharge from the active pit as well as storm runoff. The
washing wastewater is not routed to the settling pond but is
discharged onto the ground around the washing plant. A small por-
tion may drain into the settling pond. The settling pond is the
water supply for the washing operation.
The water quality samples were collected at two points
within the Rossville Quarry: the pit discharge to the settling
pond (1) and the settling pond effluent (2). The settling pond
effluent flows into a drainage ditch which flows into Dry Creek.
The Creek drains a rural, primarily agricultural watershed. Above
the quarry outfall the creek was clear (Figure 5-11), but below
the outfall (Figures 5-12 and 5-13), the creek was turbid. This
turbidity was not entirely a result of limestone quarry operations,
but rather to sediments picked up by the effluent stream prior to
the effluent stream reaching the creek. After discharge from the
final settling pond (Figure 5-14, lower right) the effluent
crosses a quarry roadbed which is traveled by large trucks. In
the process, the stream acquires a large sediment load. The
effluent is then ditched past a diesel oil storage tank (Fig-
ure 5-15), under a road, and eventually into the creek (Fig-
ure 5-16), creating a large mixing plume of sediment laden water
(Figure 5-17).
Southern Stone Company
The Maylene Quarry of Southern Stone Company is located
south of Birmingham, Alabama. This quarry consists of a 40 acre
pit and a wet crushing plant which produces about 800,000 tons
per year of dolomitic limestone products.
5-14
-------
PIT DEWATERING
QUARRY
PIT
STONE
PRODUCT
CRUSHING
SEDIMENTATION
POND
WATER
SUPPLY
PRODUCT
WASHING
DISCHARGE
TO GROUND
DRY CREEK
Figure 5-10. Process Diagram, The Stone Han, Inc., Chattanooga, Tennessee
-------
Figure 5-11. The Stone Man, Rossville Quarry
Dry Creek Upstream of Quarry
Discharge
Figure 5-12. The Stone Han, Rossville Quarry
Dry Creek Downstream of Quarry
Discharge
5-16
-------
Figure 5-13. The Stone Han» Rossville Quarry.
Dry Creek Downstream of Quarry
Discharge
Figure 5-14, The Stone-Han, Rosaville Quarry.
MtatiKHgc i.i'OUl 1-xi'ielA, cet-i.JLa.iig rwtid
(Lower right) as it crosses road
bed (Center of figure)
r* i —•
J **" JL /
-------
Figure 5-15. The Stone Man, Rossville Quarry.
Drainage Ditch (Upper left) Flow-
ing Near Oil Storage Tanks
Figure 5-16, The Stone Man, Rossville Quarry.
Drainage Ditch Immediately Upstream
of Confluence with Dry Creek
5-18
-------
The Stone Wan, Eossville Quarry.
Mixing, Zone of Sediment Laden
Quarry Discharge with Clear Dry
Creek Water
5-19
-------
Figure 5-18 is a diagram of the quarry elements and
discharge. The central element of this quarry's treatment sys-
tem is a small lake. This lake receives the pit dewatering dis-
charge from the pit sump. Water from the lake is used for wash-
ing and the wash wastewater is discharged to a sedimentation
pond which discharges back into the lake. During wet weather
the lake discharges to an intermittent creek; otherwise the
quarry has a closed cycle treatment system.
At the time that this quarry was sampled, the sedimen-
tation pond receiving wastewater from the washing plant was com-
pletely filled with sediment because the dredging equipment was
inoperative and under repair. The wash wastewater flowed over
the surface of the sediment and discharged from the pond within
a few minutes of entering. The results of the suspended solids
analyses in Section 6.1 indicate that the pond was providing
virtually no treatment to the wastewater under such operating
conditions.
The effluent from the sedimentation pond flowed into
the small lake, which was shallow near the sedimentation pond
outfall because of sediment deposition. The dam at the outfall
from the lake was enlarged with a load of fill in an attempt to
raise the water level in the lake, and there was no discharge
from the lake.
Water quality samples were collected on January 25,
1980 from the pit dewatering discharge to the lake (1), the wash-
ing supply water from the lake (2), the washing wastewater (3),
the sedimentation pond discharge (4) and from the lake near the
normal discharge point (5) (although it was not discharging at
the time).
5-20
-------
QUARRY
PIT
PIT
DEWATERING
I
STONE
CRUSHING
LAKE
WATER SUPPLY
PRODUCT
WASHING
POND
SEDIMENTATION
GRAVEL
p
5
X
DISCHARGE
POINT
Figure 5-18. Process Diagram, Southern Stone Company, Birmingham, Alabama
-------
There are two small streams draining the quarry site.
One originates at the lake outfall of the quarry, and the other
is a small ditch that originates near the railroad embankment
which borders the end of the quarry property. The stream which
originates at the quarry was dammed prior to the sample date and
was dry (Figure 5-19). The second stream is a drainage ditch
(Figure 5-20) which flows alongside the quarry stockpiles and
normally receives no discharge. At the date of sampling, there
was an inadvertent discharge from a runoff detention pond into
the drainage ditch (Figure 5-21). Downstream portions of the
ditch were affected by this discharge (Figure 5-22) but since
the ditch is intermittent in flow and already highly impacted,
1 i f* f* 1 o n ^ 1 t~-n /-\r» n | -» TOT"! /"* +* "I O 0"V*T\ QP
Jn X> ip I*' JL ci VjL \aJL JL Lv JLb W Lid Xt JLkjJUL^r i*r Jm O W W vl2» Ul ¦
At the time of sampling, both the sedimentation pond
(Figure 5-23) and the lake (Figure 5-24) were filling with sedi-
ment. They had not been dredged recently because of inoperative
dredging equipment. Oil discharges were also noted in the sedi-
mentation pond (Figure 5-25).
Both the washing sedimentation pond and the pit dis-
charges flow into a lake. This lake has extensive rooted mar-
ginal vegetation (Figure 5-26).
Flintkote Stone Products Company
The Texas Quarry of Flintkote Stone Products Company
is located in Cockeysville, Maryland. This facility was visited
twice, first on February 13 and 14, and again on July 24 and 25,
1980. This quarry has been in operation since 1927 and is one
of the largest quarries in the United States, producing approxi-
mately 3 million tons per year of limestone products. A diagram
of this operation is included as Figure 5-27. The Texas Quarry
5-22
-------
sSStS
tone Co.» Mayl
Dammed Braina,
juthern
—
lisM
Figure 5-20. Southern Stone Co., Maylene Quarry.
Drainage Ditch at Perimeter of
Quarry Property
5-23
-------
Southern Stone Co., Haylene Quarry.
Runoff Detention Pond Discharge
fnto Drainage Ditch
5-24
-------
Figure 5-21. Southern Stone Co., liny ion c Quarry,
l'i 1 led -in SeelimenmI Lnn Pond
5-23
-------
5-26
-------
Southern Stone Co., Maylene Quarry.
Emergent Ilacrophytes Near Pit
Dewaterinp Discharge
-------
t-ri
l
to
CJ
CALCITE
CALCITE
PLANT
WATER
SUPPLY
FROTHER
FLOTATION
PRODUCT
SEDIMENTATION
POND
#1
SEDIMENTATION
POND
U2
SEDIMENTATION
POND
»3
STONE
I
CRUSHING
CRUSHING
«1
*2
a
WASHING
WASHING
«1
«2
SEDIMENTATION
POND
a
PRODUCT
1
I"
Ift
0
5
z
SEDIMENTATION
POND
<
Q
DC
UJ
>
<
UJ
m
GOODWIN RUN
Figure 5-27. Process Diagram, Flintkote Stone Products Company,
Cockeysville, Maryland
-------
consists of an 80 acre open pit quarry and an underground cal-
cite mine. Plants and treatment systems include two wet crush-
ing operations, two sedimentation ponds for washwater treatment,
a calcite plant (Atlantic Carbonate) with a flotation frother
treatment discharge to a series of three sedimentation ponds,
a calcite mine water discharge and a quarry pit water discharge.
All discharges are to Goodwin Run, a tributary of Beaver Dam
Run.
Samples were taken on February 13 at the following
points:
1. raw washing wastewater influent to sedimen-
tation pond number 880 (1);
2. treated effluent from sedimentation pond
number 880 (2);
3. flotation frother effluent (3) (influent to
sedimentation pond series);
4. effluent from sedimentation pond series (4);
and
5. underground mine water discharge (5).
The pit water was not being discharged during the sampl-
ing period. The second sedimentation pond (number 874) was not
sampled because it was only receiving runoff from a watering
truck filling line which discharged onto the ground most of the
time.
5-29
-------
Goodwin Run is a small perennial urban-suburban stream
in the Loch Raven Reservoir watershed. Loch Raven Reservoir is
the primary source of drinking water for the city of Baltimore.
Goodwin Run flows through an industrial area before reaching the
quarry site (Figure 5-28) and is subjected to runoff and discharge
from industry and from areas of impermeable cover. Construction
is proceeding on a 3200 unit subdivision immediately upstream from
the quarry.
The bed of Goodwin Run upstream from the quarry site
was littered with household trash (Figure 5-29). On the plant
site, Goodwin Run is cobble bottomed upstream from the quarry
discharges (Figure 5-30) but as sediment is added (Figure 5-31),
the bottom of the creek becomes covered with a fine sediment
(Figure 5-32).
Beaver Dam Run showed no pronounced sediment accumula-
tion immediately downstream (approximately one-half mile) from
the confluence with Goodwin Run (Figure 5-33).
Oldham County Stone Company
The Oldham County Stone/Brownsboro Quarry is located
in Crestwood, Kentucky, near Louisville. This quarry, which was
sampled on February 28, 1980, produced 238,000 tons of crushed
limestone products per year in 1978 and 431,000 tons per year in
1979.
This quarry, as diagrammed in Figure 5-34, consists of
one pit with a sump discharge and a crushing plant. The crush-
ing plant, which is a dry crushing operation, was shut down for
winter maintenance. The only water discharge is pit dewatering
from the pit sump, and this discharge was sampled (1). The re-
ceiving stream is a small tributary to Harrod's Creek.
5-30
-------
Figure 5-28, Plintkote Stone Products Co.,
Texas Quarry. Goodwin Run
Upstream of Quarry Looking
Downstream
Fit-ure b -29 F1 intkot'c- Stone Product.;; Co »
Texas Quarry. Goodwin Run
Upstream of Quarry Looking
Downstream
5-31
-------
Figure 5-30
F1intkote Stone Products Co.,
Texas Quarry. Goodwin Run on
Quarry Site Upstream of First
nf
¦hhh^iihhmmb
!li^»liii!«*
Figure 5-31. Flintkote Scone Products Co.,
Texas Quarry. Goodwin Sun at
Calcite Mine Discharge
5-32
-------
Figure 5-32. Plintkote Stone Products Co.,
Texas Quarry. Goodwin .lun Up
stream of Discharge from Sed i
mentation Pond 880
h lfoiiiiMir''' '
' SMB.
mmw®.
r igurc i? ** j j . i* i jl11LRo Lc S tone rrocluc Ls Lo, ,
Texas Quarry, Beaver Dam Run
Downstream of Confluence with
Goodwin Run
3-:n
-------
POND
DAM
UJ
UJ
K
o
a
ui
DEWATERINO
PRODUCT
SUMP
QUARRY
\ PIT
DRY
CRUSHING
HARROD'S CREEK
Figure 5-34. Process Diagram, Oldhan County Stone. Company, Louisville, Kentucky
-------
The tributary is very small, arising from a pond on
the plant property and flowing one-half mile to the confluence
with Harrod's Creek. The receiving creek has a high gradient
with two small waterfalls above the junction with Harrod's
Creek,
The pond which serves as the source of the creek is
formed as an impoundment on a drainage ditch and apparently the
ditch has a loading of organic wastes as the bottom was coated
with a dense stand of blue-green and green algae,
Kentucky Stone Company
The Todd County Quarry of Kentucky Stone Company was
visited on February 29, 1980. This quarry, located near Elkton
in southwest Kentucky, produces approximately 200,000 tons per
year of crushed limestone. Product sizes range from rip-rap
to agricultural lime.
Figure 5-35 is a diagram of the quarry and discharge.
There is no washing of products, and the only discharge is from
rrn <3¦v*Y"rT ni t* otimn t.tV* "i itoc TiinAl" "(¦ flu vi nrr o t'AWi finrflTit" c
T* Jm j J* JL U b Ullip V* fXJL> Li X> w fc5 JL> V w X. wll*(•/ JL JL» JL>XLg w L> w JL111 C v vI' w b •
The discharge is to a drainage ditch, and samples of this dis-
charge were collected (1).
France Stone Company, Monroe Quarry
The France Stone Company Monroe Quarry, located in
Monroe, Michigan, was sampled on May 13, 1980. This quarry pro-
duces about 1,500,000 tons per year of crushed limestone and
stone sand.
Figure 5-36 is a diagram of the quarry and discharges.
The quarry consists of a pit and pit sump, a primary crusher, a
5-35
-------
STONE
PRODUCT
0
DRAINAGE DITCH
DRY
CRUSHING
QUARRY
PIT
i*
1°
S
z
Figure 5-35. Process Diagram, Kentucky Stone Company,
Elkton, Kentucky
-------
«_n
i
OJ
Recycle
Stone
o>
Sedimentation
Pond
a.
a.
Product
Primary
Wet
Crushing
Wet Crushing
and Screening
Quarry
1
m
jo
z
Plum Creek
Figure 5-36. Process Diagram, France Stone Company, Monroe
Quarry, Monroe, Michigan
-------
stone sand washing plant, and a wet crushing and washing mill.
Effluents from the stone sand washing and the crushed stone wash-
ing operations are discharged to one sedimentation pond. At the
time of sampling, the pond has not filled to the discharge point
due to seepage and the recent start-up of the operation. Later
in the summer, the sedimentation pond overflows and the effluent
flows to the pit sump. The sump water is used as make-up water
for washing, although excess water from seepage is discharged
daily from the sump to Plum Creek which eventually discharges into
Lake Erie. Plum Creek arises in agricultural land approximately
ten miles upstream from the quarry and flows with a low gradient
through a suburban-rural area. The creek becomes heavily loaded
with agricultural and urban runoff before arriving at the quarry.
At the time of sampling the only loading to Plum Creek from the
quarry was from pit discharge. Water samples were obtained of
the washwater supply from the sump (1), and the washing effluent
from both the stone sand washing (2) and the wet crushed stone
washing (3).
France Stone Company, Bloomville Quarry
The France Stone Company operates a quarry in Bloom-
ville, Ohio which was visited on July 23, 1980. This plant pro-
duces about 600,000 tons per year of crushed limestone in a va-
riety of products.
As represented in Figure 5-37, the quarry consists of
a 110-acre pit and sump, a crusher and a washing plant with a
total recycle sedimentation pond. The washing process was out
of operation during the time of sampling, and only the sump dis-
charge water was sampled (1). This discharge was to Eicholtz
Ditch. Existing discharges to Eicholtz Ditch are agricultural
and rural. The ditch has a small drainage area and has been
dammed downstream of the plant site to form a small lake.
5-38
-------
STONE
—o
PRODUCT
PRODUCT
RECYCLE WATER
_l
SEDIMENTATION
. POND .
SEDIMENTATION
w POND -
SUMP
WASHING
CRUSHING
QUARRY
PIT
0
5
z
Figure 5-37. Process Diagram, France Stone Company, Bloomville
Quarry, Bloomville, Ohio
-------
5,3 Self-Monitoring Historical Data
The self monitoring data collected by each company for
their permitted discharges are summarized in Table 5-3. Avail-
able data from the years 1977-1979 are included. The average of
all data indicates excellent water quality in terms of suspended
solids concentrations of effluents from these quarries' pit sumps
and sedimentation ponds>
5-40
-------
TABLE 5-3. SUMMARY OF HISTORICAL PERFORMANCE OF LIMESTONE
QUARRY DISCHARGES (for 1977-1979)
Historical Performance
Facility Discharge
(and corresponding sample
point number from
Table 5-1)
Total Suspended
Solids (mg/1)
Average Maximum
PH
(SU)1
Range
Discharge
(MGD)2
Ft. Calhoun Stone Co.
Pit Discharge (Inactive Pit) (1) 7.1 13.0 7.6-7.9 0.4
Pit Discharge (Active Pit) (2) 13.8 20.3 7.4-8.3 0.6
River Products, Inc.
Pit Discharge (1) 29.0 100.0 6.2-8.0 0.2
The Stone Man, Inc.
Pond Effluent (2) 10.4 28.0 6.7-8.0 0.8
Southern Stone Company
Pit Discharge (1) 2.3 14.5 7.3-8.2 0.3
Settling Pond (5) 2.5 6.0 7.3-8.3
Flintkote Stone Products Company
Sedimentation Pond (2) 4.5 11.0 7.0-8.0 0.5
Pit Discharge (6) 4.2 11.0 6.8-8.1 1.3
Mine (5) 29.8 134.0 7.0-8.5 1.0
Calcite Sedimentation (4) 15.7 68.0 6.7-8.0 0.3
Oldham County Stone Company
Pit Discharge (1) 5.7 25.0 6.9-8.1 0.1
Kentucky Stone Company
Pit Discharge (1) 6.6 36.4 7.2-7.8 0.2
France Stone Company, Monroe Quarry
Pit Discharge (1) 6.0 25.8 6.6-8.0 1.0
France Stone Company, Bloomville Quarry
Pit Discharge (1) 1*8 7.0 7.1-8.1 0.4
Standard Units
2Million Gallons per Day
-------
6.0 RESULTS OF SAMPLE ANALYSES
6.1 Water Quality Analyses
The water quality characteristics of the various dis-
charges and flow streams sampled are characterized in this sec-
tion. Refer to Table 5-1 for descriptions of the sampling loca-
tions to which these results correspond. The parameters analyzed
are divided into three categories .*
Physical Parameters
Total solids, total dissolved solids, total suspended
solids, silica, hardness, turbidity, and pH.
Heavy Metals
Lead, mercury, nickel, chromium, cadmium, selenium,
zinc, and iron.
Asbestos
Total fibers, chrysotile fibers.
Table 6-1 presents the results of the physical para-
meter analyses. Although there is considerable variation of re-
sults among all samples, a correlation can be seen between type
of discharge and range of concentration. Table 6-2 presents the
flat'fl A -f iti A a. A i r1 s t" ooati d c aI* f yoat'o/l 11 on f* , irt a o +¦ q ^ T.ta afo
L*€l v— u Ui. V i-VACyi JLi.1 ww wdw c tU JL i.co wJL LLC Cl UcU KS> i L j vilL t» L tJdl ^t!»U W db UC
water, and pit discharge. Untreated washing wastewaters have sig-
nificantly higher ranges (and median values) for total solids, TSS,
turbidity, and hardness, than do either treated effluents (sedi-
mentation pond effluents) or pit dewatering discharges.
6-1
-------
TABLE 6-1. PHYSICAL PARAMETERS ANALYSES RESULTS FOR
LIMESTONE QUARRY DISCHARGES
Total Silica Hardness
Solids TDS TSS Si02 as CaC03 Turbidity
Site and Sample Point (mg/1) (rag/1) (rag/1) (mg/1) (mg/1) FTU pH
Ft. Calhoun Stone Co.
1. Pit Discharge 002 951 947 3.9 8.7 550 1.5 7.66
(Inactive Pit)
2. Pit Discharge 004 673 669 4.2 11.0 440 16.0 7.63
(Active Pit)
River Products, Inc.
1. Pit Discharge 728 693 3.5 5.3 480 <1.0 7.54
Stone Man, Inc.
1. Pit Discharge 277 231 17.0 5.0 163 16.0 8.10
2. Pond Effluent 267 223 1.2 3.4 158 12.0 8.27
Southern Stone Co.
1. Pit Discharge 317 265 4.0 4.6 232 8.0 8.30
2. Washwater Supply 1,110 312 716.0 4.4 271 >250.0 8.21
(From Lake)
3. Washing Wastewater 19,700 490 15,800.0 4.5 950 >250.0 8.05
(Before Settling)
4. Settling Pond Effluent 20,800 431 18,900.0* 4.5 1,010 >250.0 7.90
(To Lake)
*This value is from a failed settling pond (completely filled with sediment) and is not used in
comparative analyses which follow. (Continued)
-------
TABLE 6-1. PHYSICAL PARAMETERS ANALYSES RESULTS FOR
LIMESTONE QUARRY DISCHARGES (Continued)
Site and Sample Point
Total
Solids
(jng/1)
TDS
(mg/1)
TSS
(mg/1)
Silica
Si02
(mg/1)
Hardness
as CaC03
(mg/1)
Turbidity
FTU
PH
5.
Lake at Discharge
Point
319
259
8.8
3.2
223
9.0
7.76
Flintkote Stone Products Co.
(February 13)
1.
Washing Wastewater
(Before Settling)
937
450
355.0
9.0
287
62.0
7.89
2.
Settling Pond Effluent
497
467
<1.0
8.5
264
10.0
7.93
3.
Frother Effluent1
(Before Detention Ponds)
44,100
177
39,600.0
5.5
9,900
>250.0
8.04
4.
Frother Detention Pond1
Discharge
245
230
3.1
2.7
170
11.0
8.07
5.
Underground Mine
Dewatering Discharge
339
269
52.0
11.0
212
30.0
8.13
Oldham County Stone
1.
Pit Discharge
606
595
<1.0
2.0
430
<1.0
8.13
(Continued)
-------
TABLE 6-1. PHYSICAL PARAMETERS ANALYSES RESULTS FOR
LIMESTONE QUARRY DISCHARGES (Continued)
Site and Sample Point
Total
Solids TDS TSS
(mg/1) (mg/1) (mg/1)
Silica Hardness
Si02 as CaC03 Turbidity
(mg/1) (mg/1) FTU .
PH
Kentucky Stone Co.
1. Pit Discharge
319
313
<1.0
2.7
150
1.5
8.28
France Stone Co., Monroe
Quarry
1. Pit Discharge
1,900
1,800
3.1
6.04
1,272
1.0
7.49
2. Mill Washing Wastewater
27,000
9,600
16,000.0
6.92
1,500
>250.0
7.34
3. Stone Washing Wastewater
7,000
1,900
4,100.0
6.64
1,350
>250.0
7.53
France Stone Co.,
Bloomville Quarry
1. Pit Discharge
802
630
2.0
0. 58
453
1.0
8.15
Flintkote Stone Products Co.
(July 24)
1. Washing Wastewater
(Before Settling)
680
392
168.0
0.88
220
32.0
7.98
2. Settling Pond Effluent
424
338
13.0
0.77
207
1.0
8.15
3. Frother Effluent1
(Before Detention Ponds)
37,631
132
11,198.0
0.62
3,500
13,400.0
8.19
(Continued)
-------
TABLE 6-1. PHYSICAL PARAMETERS ANALYSES RESULTS FOR
LIMESTONE QUARRY DISCHARGES (Continued)
Total Silica Hardness
Solids TDS TSS SiC>2 as CaC03 Turbidity
Site and Sample Point (mg/1) (mg/1) (mg/1) (mg/1) (mg/1) FTU
PH
4. Frother Detention Pond1
Discharge
268
218
19.0 0.47
133
1.0
7.86
6. Pit Discharge
532
436
62.0 0.94
253
13.0
7.89
^alcite frother operations are not typically present at limestone crushing and washing facilities.
-------
TABLE 6-2. PHYSICAL PARAMETERS ANALYSES FOR VARIOUS TYPES OF PROCESSES
Total Total
Suupunded Dissolved Hardness
Total Solids Solids Solids Turbidity as CaCOi Silica pH
Typa of Sumpla (mg/1) (i«h/1) (mg/1) (FTU) (mg/1) (mg/1) (SU)
Sedimentation Fond Effluent
(4 samples)
Rungo 267-497 <1-13.0 223-467 1-12 158-264 0.8-8.5 7.76-8.15
Median 372 5 299 9 219 3.3
Untreated Washing Wastewater
(5 samples)
Range 680-27,000 168-16,000 392-9,600 32->250 220-1,500 0.9-9.0 7.34-8.05
7^ Mudlan 7,000 4,100 490 >250 950 6.6
cr>
Pit Dewaterlng Discharge
(10 samples)
Range 277-1,900 <1-62 231-1,800 <1-16 150-1,272 0.6-11.0 7.49-8.30
Median 640 3.7 613 1.5 435 4.8
-------
The results of the heavy metals analyses are presented in
Tables 6-3 through 6-10. Metal concentrations were analyzed by atomic
absorption (AA) and inductively coupled plasma optical spectrometer
(ICR). In some cases the results for the same sample differed by more
than an order of magnitude between the two methods of analysis. Possible
explanations for such variations include the inaccuracies which occur at
such low concentration levels as are found in these samples, inter-elemental
interference which can occur in the ICP method, and possible ICP inaccuracies..
Due to the general high integrity of the AA method of metals
analysis, only AA results are summarized in Table 6-11. The results of
analyses by AA are presented in Table 6-11 and have again been divided
into various categories of discharge types. The laboratory results from
the last two quarries sampled (Flintkote Stone Products Co. and France
Stone Co., Bloomville Quarry) are not included in this summary table
because the detection limits for these samples were higher than the
water quality criteria to which the results are being compared. As a
result, these high detection limits interfere with the comparative analysis.
Another note concerning Table 6-11 is that a number of different laboratories
performed the analyses of samples collected at the quarries. The detection
limits used in the analyses varied among the labs such that the reported
results for some metals may simply range from one detection limit to
another.
Iron appears to be the only element where significant concentrations
have occurred in all three processes. Especially high concentrations
appear in the untreated wastewater (before sedimentation) as total iron.
By comparing the high total iron with the low dissolved iron in the
untreated wastewater category, it can be seen that almost all of the
iron is in the particulate form.
6-7
-------
TABLE 6—3. ANALYSES RESULTS — LEAD
Quarry
Sample
Point*
Concentrations of Lead (mg/1)
Total
PES
AAS
Dissolved
PES
AAS
Ft. Calhoun Stone
Company
River Products, Inc.
Stone Man, Inc.
Southern Stone Co.
Flintkote Stone
Products Co.
(February 13)
Oldham County Stone
Company
Kentucky Stone Co.
France Stone Co.
Monroe Quarry
France Stone Co.
Bloomville Quarry
Flintkote Stone
(July 24)
1
2
1
2
1
2
3
4
5
1
2
3
4
5
1
1
1
2
3
1
2
3
4
6
.059
.042
.035
.033
.049
.094
.057
1.550
1.040
.121
.120
<.040
5.170
<.040
<.040
.040
.028
.042
.252
.828
<.050
<.050
<.050
<.050
<•050
<.050
<•050
<.050
<.030
<.025
<.025
<.025
<.025
.110
.184
<.025
<•050
<.050
.130
<.050
<•050
<.030
<.030
<.030
<•030
.060
.110
.130
<.100
<. 100
<.100
<.100
091
070
042
198
062
110
040
144
040
116
040
048
040
040
040
.028
.032
.058
.069
.080
<.050
<.050
<.050
<.050
<.050
<.050
<.050
<.050
<.030
.035
<. 025
<.025
<. 025
<.025
<.025
<.025
<.050
.250
<.050
<.050
<.050
<.030
<.030
<.030
<.030
<.030
.110
<.100
<.100
<.100
<.100
<•100
*Refer to Table 5-1.
6-8
-------
TABLE 6-4. METALS ANALYSES RESULTS - MERCURY
Concentrations of Mercury**
(mg/1)
Sample Total Dissolved
Quarry Point* AAS AAS
Ft. Calhoun Stone Co.
1
.001
.001
2
<.001
<.001
River Products, Inc.
1
<•001
<.001
Stone Man, Inc.
1
<.001
<.001
2
<.001
<.001
Southern Stone Co.
1
<.001
<.001
2
<.001
<•001
3
.001
<.001
4
.001
<,001
5
<.001
<.001
Flintkote Stone Products
Co.
1
<.001
<.001
(February 13)
2
<.001
<.001
3
<•001
<•001
4
<•001
<.001
5
<-001
<.001
Oldham County Stone Co.
1
<.002
<.002
Kentucky Stone Co.
1
<.002
<.002
France Stone Co.
1
<.001
<•001
Monroe Quarry
2
<.001
<.001
3
<.001
<.001
France Stone Co.
Bloomville Quarry
1
<.0006
<.0006
Flintkote Stone Products
Go.
1
<.0006
<.0006
(July 24)
2
<.0006
<.0006
3
<.0006
<.0006
4
<.0006
<.0006
6
<.0006
<.0006
*Refer to Table 5-1.
**Analyzed by AAS only.
6-9
-------
TABLE 6-5. ANALYSES RESULTS - NICKEL
Quarry
Sample
Point*
Concentrations of Nickel (mg/1)
Total
PES
AAS
Dissolved
PES
AAS
It. Calhoun Stone
Co.
River Products, Inc.
Stone Man, Inc.
Southern Stone Co.
Flintkote Stone
Products Co.
(February 13)
Oldham County Stone Co.
Kentucky Stone Co.
France Stone Co.
Monroe Quarry
1
2
1
2
1
2
3
4
5
1
2
3
4
5
1
2
3
.052
.039
.284
.127
.135
<.005
.053
.332
.246
<•005
.021
.007
.436
.018
.018
.165
.085
.492
.879
1.463
:.040
.040
.040
030
030
013
017
177
215
013
013
013
108
<.013
<.013
<.004
<.004
.050
.030
.115
058
055
280
145
147
005
020
005
031
005
.010
.020
<.005
< .005
.012
.155
.082
.539
.540
.574
<.040
.051
.040
.030
.030
<.013
<-013
<.013
.014
<.036
<.013
<.013
<.013
.014
<.013
<.004
<.004
<.030
<.030
.035
France Stone Co.
Bloomville Quarry
Flintkote Stone
Products Co.
(July 24)
1
2
3
4
6
<.050
<.050
.050
.080
.050
.050
<.100
<•100
<.100
.180
<.100
<.100
<.050
<•050
<.050
<.050
<.050
<.050
<.100
<.100
<.100
<.100
<.100
<.100
*Refer to Table 5-1.
6-10
-------
TABLE 6-6. METALS ANALYSES RESULTS - CHROMIUM
Concentrations of Chromium (mg/1)
Total Dissolved
Quarry
~ auipxt:
Point*
PES
AAS
PES
AAS
Ft. Calhoun Stone Co.
1
.016
<.030
.019
<.030
2
.007
<.030
.017
<.030
River Products, Inc.
1
.035
<.004
.035
<.004
Stone Man, Inc.
1
.012
<.020
.013
<•020
2
.013
<.020
.013
<.020
Southern Stone Co.
1
<.001
<.015
<.001
<.015
2
.047
.058
.008
<.015
3
.545
.168
<.001
.016
4
.387
.202
.009
<.015
5
<.001
<•015
<.001
<.015
Flintkote Stone
1
.023
<.004
.007
<.004
Products Co.
2
.012
<•004
.014
.015
(February 13)
3
.316
.124
<.001
<.004
4
.009
<.004
<.001
<.004
5
.010
<.004
.005
<.004
Oldham County Stone Co
. 1
.037
<.020
.037
<•020
Kentucky Stone Co.
1
.015
<.020
.014
<.020
France Stone Co.
1
.052
<.050
.055
<.050
Monroe Quarry
2
.201
<.050
.062
< .050
3
.414
<•050
.061
<.050
France Stone Co.
Bloomville Quarry
1
<.010
<.100
<.010
<•100
Flintkote Stone
1
<.010
<.100
<.010
<.100
Products Co.
2
<.010
<-100
<.010
<.100
(July 24)
3
.074
.180
<.010
<.100
4
<.010
<•100
<.010
<.100
6
<.010
<.100
<.010
<.100
*Refer to Table 5-1.
6-11
-------
TABLE 6-7. METALS ANALYSES RESULTS - CADMIUM
Concentrations of Cadmium (mg/1)
Quarry
Sample
Point*
Total
PES
MS
Dissolved
PES
AAS
Ft. Calhoun Stone Co.
River Products, Inc.
Stone Man, Inc.
Southern Stone Co.
Flintkote Stone
Products Co.
(February 13)
Oldham County Stone Co.
Kentucky Stone Co.
France Stone Co.
Monroe Quarry
France Stone Co.
Bloomville Quarry
Flintkote Stone
Products Co.
(July 24)
1
2
1
2
1
2
3
4
5
1
2
3
4
5
1
1
1
2
3
1
2
3
4
6
<.002
<.002
.002
.002
.004
<.002
<.002
.054
.036
<.002
.012
.007
.388
.006
.006
<.001
.001
<.001
.010
.044
<.005
< .005
<.005
<•005
<.005
<.005
<.005
<.005
<.003
.004
<.004
<.005
<.005
<.005
<•005
<.005
<.005
<.005
<.005
<.005
<.005
<.004
<.004
<.003
.003
<•003
<.020
<.020
<.020
<.020
<.020
<.020
.003
<.002
.003
.007
.005
<.002
<•002
<.002
< .002
<.002
.008
.010
.007
.005
.007
<.001
.001
.001
.002
.005
<.005
.005
,005
,005
,005
,005
<•005
<.005
<.003
<.004
.004
<.005
<.005
<.005
<.005
<.005
<.005
<.005
<.005
<.005
<.005
<.004
<.004
. 006
<•003
<.003
<.020
<.020
<.020
<.020
<.020
<•020
*Refer to Table 5-1.
6-12
-------
TABLE 6-8. METALS ANALYSES RESULTS - SELENIUM
Concentrations of Selenium**
(mg/1)
Sample Total Dissolved
Quarry Point* AAS AAS
Ft. Calhoun Stone Co.
River Products, Inc.
Stone Man, Inc.
Southern Stone Co.
Flintkote Stone Products Co.
(February 13)
Oldham County Stone Co.
Kentucky Stone Co.
France Stone Co,
Monroe Quarry
France Stone Co.
Bloomville Quarry
Flintkote Stone Products Co.
(July 24)
*Refer to Table 5-1.
**Analyzed by AAS only.
1 .010 .010
2 .006 .004
1 <.005 <.005
1 <.005 <.005
2 <.005 <.005
1 <.001 <.001
2 .001 <.001
3 <.001 <.001
4 .002 <.001
5 <.001 <.001
1 <.001 <.001
2 <.001 <.001
3 .006 .002
4 <.001 <.001
5 .002 <.001
1 <.003 <.003
1 <.003 <.003
1 <.005 <.005
2 <.005 <.005
3 <.005 <.005
1 <.010 <.010
1 <.010 <.010
2 <.010 <.010
3 <.010 <.010
4 <.010 <.010
6 <.010 <.010
6-13
-------
TABLE 6-9. METALS ANALYSES RESULTS - ZINC
Concentrations of Zinc (tug/1)
Total Dissolved
Sample
Quarry Point* PES AAS PES AAS
Ft. Calhoun Stone Co.
1
.024
016
.035
.019
2
.013
<
013
.020
.080
River Products, Inc.
1
.034
<
004
.025
<.004
Stone Man, Inc.
1
.025
<
005
.043
<.005
2
.036
015
.072
.005
Southern Stone Co.
1
.001
025
<.001
<.013
2
.112
103
.008
<.013
3
.395
141
.005
.029
4
.282
164
.009
.026
5
.001
<
013
<.001
.026
Flintkote Stone
1
.040
<
010
.018
<.010
Products Co.
2
.015
<
010
. 028
<.010
(February 13)
3
.528
286
.007
<.010
4
.015
<
010
.010
<.010
5
.014
<
010
.021
.015
Oldham County Stone Co.
1
.047
012
<.001
<.007
Kentucky Stone Co.
1
.013
017
.032
.022
France Stone Co.
1
.041
013
.040
.023
Monroe Quarry
2
.183
126
.116
.014
3
.203
078
.051
.010
France Stone Co.
Bloomville Quarry
1
<•010
<
020
<.010
<.020
Flintkote Stone
1
<.010
<
020
<.010
<.020
Products Co.
2
.039
044
<.010
<.020
(July 24)
3
.180
240
<,010
<.020
4
.040
038
<.010
<.020
6
.010
<.020
<.010
<.020
ARefer to Table 5-1.
6-14
-------
TABLE 6-10. METALS ANALYSES RESULTS - IRON
Quarry
Sample
Point*
Concentrations of Iron (mg/1)
Total
Dissolved
PES
AAS
PES
AAS
Ft. Calhoun Stone Co.
River Products, Inc.
Stone Man, Inc.
Southern Stone Co.
Flintkote Stone
Products Co.
(February 13)
Oldham County Stone Co.
Kentucky Stone Co.
France Stone Co.
Monroe Quarry
France Stone Co.
Bloomville Quarry
Flintkote Stone
Products Co.
(July 24)
*Refer to Table 5-1.
1
2
1
2
1
2
3
4
5
1
2
3
4
5
1
2
3
1
2
3
4
6
.117
.539
.094
.207
. 108
<•001
5.230
89.900
68.800
<.001
1.800
.035
68.700
.146
.023
.135
.113
.123
6.570
40.500
.090
1.390
.090
82.200
.450
.140
.214
.272
.168
.190
.120
.052
88.800
81.000
258.000
.083
1.470
<.100
70.000
.164
<.100
.130
.110
.110
8.670
37.000
.110
1.480
.110
79.200
.480
.170
001
001
027
028
024
001
072
001
008
001
056
031
006
001
001
089
032
063
136
055
042
030
030
030
030
<.030
<.100
.137
.107
.050
.035
<•100
<.100
<.100
<.100
<.100
<.100
<.100
<.100
<.100
<.100
.030
.050
.060
<.025
.030
<.100
<.100
<•100
<.100
<.100
<.100
6-15
-------
TABLE 6-11. RANGE OF HEAVY METAL CONCENTRATIONS ANALYSES
FOR VARIOUS TYPES OF PROCESSES* (Concentrations
in mg/1, Atomic Absorption Spectrometer Method)
Pit Sedimentation Untreated
Dewatering Pond Washing
Discharge Effluent Wastewater
Heavy
Metal Min Max Min Max Min Max
Lead
Total
<.025
-
<
.050
<.025
_
<.050
<.030
-
.110
Dissolved
<.025
-
<
.050
<•025
-
.250
<.025
-
<.050
Mercury
Total
<.001
_
<
.002
<,001**
<.001
-
.001
Dissolved
<.001
-
<
.002
<.001**
<.001**
Nickel
Total
<.004
-
050
<-013
-
<.030
<.013
-
.177
Dissolved
<.004
-
051
<.013
-
.036
<.013
-
.035
Chromium
Total
<.004
-
<
050
<•004
-
<.020
<.004
_
.168
Dissolved
<.004
-
<
050
<.015
-
<.020
<.004
-
<.050
Cadmium
Total
<.003
-
<
005
<.004
-
<,005
<.003
-
<.005
Dissolved
<.003
_
006
.004
-
<.005
<.003
_
<.005
Selenium
Total
<.001
-
010
<.001
-
<.005
<.001
-
<.005
Dissolved
<.001
-
010
<.001
_
<.005
<•001
-
<.005
Zinc
Total
<.004
-
025
<•010
-
.015
<.010
-
.141
Dissolved
<•004
-
080
.005
-
.026
<-010
-
.029
Iron
Total
.052
_
272
.083
-
.120
1.470
_
81.00
Dissolved
.030
—
137
.035
—
<.100
<.025
—
<.100
~Samples from the quarries were analyzed by a number of different laboratories.
Detection limits varied from lab to lab for the same parameter.
**A11 values were reported as <.001.
6-16
-------
form. By comparing total iron in the untreated wastewater with
total iron in the treated wastewater (sedimentation pond effluent),
it is also evident that a very high percentage of the iron is
removed by sedimentation ponds. Other than iron, the heavy me-
tals are primarily in the dissolved form.
Table 6-12 presents the asbestos analyses results.
From this table it can be seen that half of the quarries sampled
contained detectable concentrations of chrysotile asbestos fiber.
It can also be seen that sedimentation ponds remove a very high
percentage of these fibers. For the February 13 visit, compari-
son of Flintkote sample point 1 with sample point 2 shows a 977,,
removal and point 3 to point 4 also shows a 977, removal for total
chrysotile fibers.
6.2 Ecological Analyses
6.2.1 Ft, Calhoun Stone Company
Both quarry pits were being pumped during the time of
sampling. No plankton was present in either of the discharge
channels. Drainage channel 002 had extensive stands of dry cat-
tails (Typha) and knotweed (Polygonum) from the previous growing
season.
The total suspended solids of the 002 channel, <10 mg/1,
was lower than the TSS of the Missouri River (Table 6-13). The
TSS of channel 004, 28 mg/1 (Table 6-13), was higher than the ri-
ver water because of sediments scoured from the bottom of the
drainage channel.
No biological samples were taken of the Missouri River
because of adverse ice conditions. It is expected that the im-
pacts to the Missouri River from Calhoun Stone Company are minimal
because of the large volume and turbid nature of the river.
6-17
-------
TABLE 6-12. CONCENTRATIONS OF ASBESTOS FIBERS OCCURRING
IN WATER AT LIMESTONE MINES (All concentra-
tions are expressed in units of million
fibers per liter)
Site and
Sampling
Point
Total
Fibers
(all sizes)
Chrysotile
Fibers
(all sizes)
Total
Fibers
(restricted
sizes)*
Chrysotile
Fibers
(restricted
sizes)*
Detection
Limit
Ft. Calhoun Stone Co.
1.
Pit Discharge
(Inactive Pit)
2.3
ND
ND
ND
0.5
2.
Pit Discharge
(Active Pit)
10.1
ND
ND
ND
0.7
River
Products, Inc.
1.
Pit Discharge
ND
ND
ND
ND
0.7
Stone
Man, Inc.
1.
Pit Dewatering
2.6
ND
ND
ND
0.4
2.
Pond Effluent
7.2
1.1
0.4
0.4
0.4
Flintkote Stone Pro-
ducts Co.
(February 13)
1.
Washing Wastewater
430.0
330.0
54.4
46.0
4.2
2.
Settling Pond
Effluent
23.3
9.7
1.8
1.2
0.2
(Continued)
-------
TABLE 6-12. CONCENTRATIONS OF ASBESTOS FIBERS OCCURRING
IN WATER AT LIMESTONE MINES (All concentra-
tions are expressed in units of million
fibers per liter) (Continued)
Site and
Sampling
Point
Total
Fibers
(all sizes)
Chrysotile
Fibers
(all sizes)
Total
Fibers
(restricted
sizes)*
Chrysotile
Fibers
(restricted
sizes)*
Detection
Limit
3.
Frother Effluent
1 76.8
J 18.8
2.3
0.8
0.8
4.
Frother Deten-
tion Pond1
8.7
0.5
ND
ND
0.2
5.
Underground Mine
Dewatering Dis-
charge
120.0
77.9
11.3
11.3
1.1
Oldham County Stone
1.
Pit Discharge
2.5
ND
ND
ND
0.1
Kentucky Stone Co.
1.
Pit Discharge
16.0
0.3
ND
ND
0.3
France Stone Co.
Monroe Quarry
1.
Pit Discharge
1.13
ND
ND
ND
0.09
2.
Mill Washing
Wastewater
835.0
390.0
ND
ND
56.0
3.
Stone Washing
Wastewater
1.6
0.5
ND
ND
0.5
(Continued)
-------
TABLE 6-12. CONCENTRATIONS OF ASBESTOS FIBERS OCCURRING
IN WATER AT LIMESTONE MINES (All concentra-
tions are expressed in units of million
fibers per liter) (Continued)
Site and
Sampling
Point
Total
Fibers
(all sizes)
Chrysotile
Fibers
(all sizes)
Total
Fibers
(restricted
sizes)*
Chrysotile
Fibers
(restricted
sizes)*
Detection
Limit
France Stone Co.
Bloomville Quarry
1.
Pit Discharge
0.56
ND
ND
ND
0.07
Flintkote Stone Pro-
ducts Co.
(July 24)
2 .
Settling Pond
Effluent
2.1
0.14
ND
ND
0.07
4 .
Frother Detention
Pond1
7.7
0.35
ND
ND
0.35
6 .
Pit Discharge
50.74
ND
ND
ND
0.43
*Restricted sizes are fibers less than 0.5 mm in diameter and greater than 5 mm in length.
ND - None Detected
'Calcite frother operations are not typically present at limestone crushing and washing facilities.
-------
TABLE 6-13. FT. CALHOUN STONE CO.
FT. CALHOUN, NEBRASKA
DECEMBER 17-18, 1979
RECEIVING STREAM - MISSOURI RIVER
Total
Dissolved Suspended
Depth Temperature Conductivity Oxygen ORP Solids1
Station (meters) ("Centigrade) (mmhos/cm) (ppm) pH (mv) (mg/1)
0022 - - - <10
0042 - - - 28
Missouri River (upstream of quarry)3 21
^ach method (photometric).
Measurements of 002 and 004 waters were not made because these streams are short, man-made ditches
with little biota.
Measurements of Missouri River waters were not made because the size of this river made detailed
assessment of impacts infeasible.
-------
6.2.2 River City Products
The River City Products quarry has one discharge into
the Iowa River. Planktonic, benthic and water samples were taken
above and below the outfall. Dissolved oxygen, conductivity, tem-
perature and total suspended solids were not significantly dif-
ferent above and below the outfall (Table 6-14). Plankton above
and below the outfall were also similar. The phytoplankton was
1 • ^ A J[ — J » .. . A -.Am'-.— J —.11 I" „ _ — — -C
dominated by a diatom, Astenone1la tormosa. Other species or
phytoplankton included Tabellaria sp., Nitzschia spp. , Stephano—
discus sp., Cyclotella sp., and an unidentified euglenoid. Zoo-
plankton was sparse and consisted mainly of a rotifer, Keratella,
with a minor component of an unidentified cladoceran.
The TSS of the discharge of 11 mg/1 was lower than that
of the Iowa River. This discharge is often of higher quality
than the Iowa River (Table 6-15), and no adverse impacts to the
river were found or are expected at current levels and quality
of discharge.
6.2.3 The Stone Man, Inc.
The quarry's combined pit and washing wastes are dis-
charged to a small drainage ditch which empties into Dry Creek.
The creek immediately upstream from the discharge had a total
suspended solids load of less than 10 mg/1 (Table 6-16) while
the drainage ditch had a total suspended solids load of 465 mg/1.
The downstream combined TSS load was 130 mg/1. This is an order
of magnitude increase in the sediment load of Dry Creek as the
discharge from the Stone Man joins it. Conductivity also rises
in the creek from 0.19 mmhos/cm above the ditch to 0.23 below
the ditch. Dry Creek was visibly affected by the discharge but
no biological effects were evident.
6-22
-------
TABLE 6-14. RIVER CITY PRODUCTS
IOWA CITY, IOWA
DECEMBER 19, 1979
RECEIVING STREAM - IOWA RIVER
Total
Dissolved Suspended
Depth Temperature Conductivity Oxygen ORP Solids1
Station (meters) (°Centigrade) (mmhos/cm) (ppm) pH (mv) (mg/1)
Iowa River Up-
stream of Quarry Surface 2.1 .223 6.35 —2 —2 11
Iowa River Down-
stream of Quarry Surface 2.2 .230 6.27 —2 —2 11
^ach method (photometric)
2Equipment malfunction
-------
TABLE 6-15. SUSPENDED SEDIMENTS OF THE IOWA RI¥ER
AMD CONKLIN QUARRY EFFLUENT*
Total Suspended Sediment (mg/1)
Iowa River Quarry
Date (At Quarry Water Intake) Discharge
8/31/80 50 18
9/25/80 20 12
11/26/80 34 11
*River City Products Data.
6-24
-------
TABLE 6-16. THE STONE MAN, INC.
CHATTANOOGA, TENNESSEE
JANUARY 24, 1980
RECEIVING STREAM - DRY CREEK
Station
Depth
(meters)
Temperature
("Centigrade)
Conductivity
(mmhos/cm)
Dissolved
Oxygen
(ppm)
PH
ORP
(mv)
Total
Suspended
Solids1
(mg/1)
Drainage ditch
from plant
0.3
7.8
0.30
10.85
8.79 314
465
Upstream of dis-
charge on Dry
Creek
0.4
9.0
0.19
10.65
8.30 326
<10
Partial mixing
zone
0.9
8.5
0.21
10.69
8.49 322
222
Upstream of dis-
charge point
(backwash)
0.5
9.0
0.19
10.60
8.32 323
16
Downstream of dis-
charge point
(in mixed region)
0.5
8.8
0.23
10.50
8.50 312
130
Pit
0.6
7.5
0.40
11.72
8.89 258
45
^ach method (photometric)
-------
There were no phytoplankton or zooplankton in the creek
at the site. Macrophytic algae consisted of mats of Cladophora
sp. heavily epiphytized by Cocconeis sp., with a few colonies of
Synedra sp. Some chains of Melosira sp. were also found inter-
twined with the Cladophora. The Cocconeis sp. epiphyte occurred
on stands of Cladophora sp. both above and below the drainage
ditch outfall. Either the sediment addition from this ditch was
temporary or it does not affect either the Cladophora sp. or
Cocconeis sp. Most probably it was a temporary addition.
The only benthic invertebrate found in Dry Creek was a
decapod crustacean Qrconectes sp.
6.2.4 Southern Stone Co.
This quarry discharges to an unnamed creek. The quarry
pond is the headwater of the creek, but at the time of our visit,
the creek was dammed. The dried bed of the creek was covered
with the remnants of last year's bloom of duckweed (Lemna sp.).
A second drainage ditch runs by the perimeter of the plant and
receives some discharge from the washing operation.
The pond on the quarry site had a relatively high pH
(Table 6-17) and had a flora typical of hardwater. The dominant
aquatic plant was Chara sp., a member of the Charophyta charac-
teristic of hard waters. Alga mats near the perimeter of the
pond were composed of Ulothrix sp., Spirogyra sp., and Zygnema
sp., filamentous green algae typical of mildly eutrophic still
waters. Phytoplankton was sparse. The diatom Nitzschia sp. and
the euglenoid Euglena sp. were present. The benthic fauna was
composed of Odonata, dragonfly and damselfly nymphs. In the
Zygoptera (damselfly nymphs) both Erythodiplax sp. and Ferithemis
occurred. The Anisoptera (dragonflies) were represented by
Gynacantha sp.
6-26
-------
TABLE 6-17. SOUTHERN STONE COMPANY
BIRMINGHAM, ALABAMA
JANUARY 25, 1980
RECEIVING STREAM - UNNAMED
Station
Depth
(meters)
Temperature
("Centigrade)
Conductivity
(mmhos/cm)
Dissolved
Oxygen
(ppm)
PH
ORP
(mv)
Total
Suspended
Solids1
(mg/1)
Pit discharge
0.5
10.6
0.44
10.50
8.51 316
4.0
Lake (near pre-
vious discharge)
0.5
11.0
0.57
10.42
8.68 310
8.8
Gravimetric method
-------
Quarry workers reported that the pond supported bass,
bluegills and catfish and that the pond was fished regularly.
6.2.5 Flintkote Stone Products, 13 February 1980
The Flintkote quarry discharges calcite mine, froth
flotation, physical plant, and settled washing effluents into
Goodwin Run, a tributary of Beaver Dam Run. Beaver Dam Run
empties directly into Loch Raven Reservoir, the primary source
of drinking water for the city of Baltimore. Upstream from the
quarry, Goodwin Run is cobble and gravel bottomed, downstream
there is a noticeable sediment, apparently finely divided cal-
cite, covering the cobble.
Suspended sediment loads in Goodwin Run at the time of
this sampling increased slightly as the creek passed through the
quarry. Upstream values were 15 mg/1 TSS while below the 880
settling pond the TSS was 18 mg/1. Conductivity increased signi-
ficantly from 0.27 mmhos/cm upstream to 0.46 mmhos/cm downstream
(Table 6-18).
There was a pronounced change in the periphytic and
attached algal flora as the creek passed through the quarry.
Upstream from the quarry the algal community was dominated quite
strongly by the chain forming diatom, Diatoma sp. The diatom
community associated with the Diatoma was composed of a tube-
forming Cymbella sp., chain-forming Melosira sp. and tufts of
Synedra sp. with interspersed Nitzschia sp. This abundant
diatom flora was completely replaced downstream of the froth flo-
tation outfall by a flora dominated by Cladophora sp., a filamen-
tous green alga, some species of which are characteristic of
stressed communities. Most species of the periphytic diatom
community were encountered in the plankton downstream. The cause
6-28
-------
TABLE 6-18. FLINTKOTE STONE PRODUCTS, TEXAS QUARRY
COCKEYSVILLE, MARYLAND
FEBRUARY 13-14, 1980
RECEIVING STREAM - GOODWIN RUN
Station
Depth
(meters)
Temperature
("Centigrade)
Conductivity
(mmhos/cm)
Dissolved
Oxygen
(ppm)
PH
ORP
(mv)
Total
Suspended
Solids1'2
(mg/1)
Goodwin Run up-
stream from plant 0.3
Calcite discharge
At outfall of under-
ground portion of
stream 0.3
Inlet to 880 pond 0.2
Outlet of 880 pond -
Goodwin Run below
last quarry dis-
charge 0.5
Beaver Dam Run be-
low confluence with
Goodwin Run 0.6
1.8
0.27
13.95
8.50 292
4.5
5.5
2.1
3.9
3.1
0.23 12.52 8.00 239
0.80 11.62 8.05 255
0.83 12.85 8.14 254
0.46
0.16
12.28
12.52
8.97 217
7.65 288
15''
52
12
355
<1.0!
18
10'
Gravimetric method
2Hach method (photometric)
-------
of the shift in communities is undetermined, however heavy coat-
ings of sediment were found on the downstream stands of Cladophora
(Figure 6-1) while this sediment was absent upstream.
The benthic fauna of the upstream reaches of Goodwin
Run was composed mainly of Tendipes sp. larvae, Goodwin Run be-
low the last quarry discharge has a shifting sand bottom and the
Tendiped fauna was absent. No other macroinvertebrates were
found in the winter collections.
6.2.6 Oldham Stone Co.
The Oldham Stone Co. quarry discharges into an unnamed
tributary of Harrod's Creek. At the time of sampling the quarry
was discharging pit dewatering only.
There was a rise in total suspended solids from 4.0 mg/1
above the discharge to 25 mg/1 below the discharge (Table 6-19).
Conductivity also rose from 0.19 mmhos/cm above the discharge to
0.65 mmhos/cm directly below the discharge. The algae of the
tributary were characterized by a Diatoma/Stigeoclonium flora
(Table 6-2 0).
Diatoma is a periphytic chain-forming diatom. Stigeo-
cIonium is a much branched filamentous green alga characteristic
of eutrophic waters. There was no detectable difference between
the flora upstream from the quarry outfall arid that found down-
stream.
Benthic invertebrates consisted of Oligochaetes,
Caddisfly larvae and Tendiped larvae; no differences in benthic
fauna were noted between stations above the quarry outfall and
stations below the.outfall.
6-30
-------
Figure 6-1. F1intkote Stone Products Co.,
Texas Quarry. Cladophora sp.
Covered with Se31jmerit Irrtme-
diately Upstream of Sedimenta-
tion Pond 380 Discharge
6-31
-------
TABLE 6-19. OLDHAM STONE COMPANY
LOUISVILLE, KENTUCKY
FEBRUARY 28, 1980
RECEIVING STREAM - TRIBUTARY TO HARROD'S CREEK
Total
Dissolved Suspended
Depth Temperature Conductivity Oxygen ORP Solids1
Station (meters) ("Centigrade) (mmhos/cm) (ppm) pH (mv) (mg/1)
Upstream of pit dis-
charge
0.3
5.1
0.19
12.90
9.05 176
4.0
Downstream of pit
discharge 0.2
Harrod's Creek
upstream of con- 0.2
fluence with
tributary
Harrod's Creek
downstream of con- 0.3
fluence with
tributary
6.9
8.4
7.8
0.65
0.39
0.50
10.85
12.25
11.29
8.15 246
8.43 245
8.33 249
25
22
Gravimetric method
-------
TABLE 6-20. ALGAE OF THE UNNAMED TRIBUTARY
TO HARROD'S CREEK - FEBRUARY 28,
1980
Baeillariophyta (diatoms)
Dtatoma sp. (codominant)
Cymbella sp, (subdominant)
Tabellaria sp.
Nitzschia sp.
Nitzschia sp. (bicapitate)
Campylodiscus
Rhoicosphenia curvata
Amphora sp.
Cocconeis sp.
Surirella sp.
Chlorophyta (green algae)
Stigeoclonium sp. (filamentous codominant)
unidentified volvocalean alga
Cyanochloronta (blue green algae)
Nodularis sp.
Gloeocapsa sp.
6-33
-------
6.2.7 Kentucky Stone Company
The Kentucky Stone Company quarry effluent is composed
of pit discharges only. There is no discharge from the crushing
operation. Discharge is to an unnamed drainage ditch. The ditch
is ephemeral, and at the time of sampling was running due to re-
cent rainfall. Phytoplankton was composed of Cocconeis sp.,
Opephora sp., and Navicula sp., all diatoms. An unidentified
tintinnid was also present in the plankton. Total suspended
sediment in the stream was 18 mg/i (Table 6-21).
6.2.8 France Stone Company, Monroe, Michigan
The France Stone Company quarry discharges to Plum
Creek. The creek was apparently heavily loaded with agricultural
and urban loadings at the time of sampling. Water quality mea-
surements were made at four upstream stations, at the discharge
point, and at one station downstream from the quarry discharge.
Conductivity rose as one progressed downstream (Table 6-22).
Total suspended solids increased slightly at the downstream sta-
tions; the pit discharge, however, had a lower sediment load than
Plum Creek upstream of the discharge.. The discharge increased
the dissolved oxygen in Plum Creek.
The biota of the stream were typical of eutrophic mid-
west streams. The algal community was completely dominated by
Cladophora sp., a filamentous green alga. The diatoms, Cocconeis
sp.. Gyrosigma sp. and numerous species of Nitzschia also oc-
F > _/.r P r — —— r — ~ ^~ Z-l
curred. The Cladophora was covered with a stalked diatom, Cymbella.
The benthic invertebrate community was dominated by the
bloodworm, Tendipes sp.; leeches, Macrobdella sp.; freshwater
limpets, Ferrissia sp.; clams, Sphaerium sp.; snails Ammicola sp.;
6-34
-------
TABLE 6-21. KENTUCKY STONE COMPANY
TODD CO. QUARRY
ELKTON, KENTUCKY
FEBRUARY 29, 1980
RECEIVING STREAM - UNNAMED
Station
Depth
(meters)
Temperature
("Centigrade)
Conductivity
(mmhos/cm)
Dissolved
Oxygen
(ppm)
PH
ORP
(mv)
Total
Suspended
Solids1
(mg/1)
Receiving Stream
18
^ach method (photometric)
Measurements of receiving stream were not made because the stream is a man-made ditch with little
biota.
-------
TABLE 6-22. FRANCE STONE COMPANY
MONROE, MICHIGAN
MAY 12-13, 1980
RECEIVING STREAM - PLUM CREEK
Station
Depth
(meters)
Temperature
("Centigrade)
Dissolved
Conductivity Oxygen ORP
(mmhos/cm) (ppm) pH (mv)
Total
Suspended
Solids1'2
(mg/1)
Strasburg Road
Bridge (upstream
of discharge)
Rasinville Road
Bridge (upstream of
discharge)
0.1
0.3
14.3
14.2
0.70
0.84
6.15
7.07
7.57 309
7.65 310
102
12'
Herr Road Bridge 0.2
(upstream of dis-
charge)
M 125 Bridge (up- 0.3
stream of discharge)
Pit Discharge 0.1
LaPlaisance 0.1
Road Bridge (down-
stream of discharge)
13.9
14.2
17.2
15.3
0.88
1.07
1.08
1.04
6.22
6.61
11.58
9.96
7.74 306
7.75 288
8.20
8.15
244
265
12'
13'
13
3.1
2
1Gravimetric method
2Hach method (photometric)
-------
and an unidentified isopod were also found.
6.2.9 France Stone Company, Bloomville, Ohio
The France Stone Company quarry at Bloomvi1le, Ohio empties
into Eicholtz Creek, On the day of sampling, the creek was turbid because
of recent rains. Total suspended solids ranged from 65 mg/1 Immediately
above the quarry discharge to 76 rag/1 below the discharge (Table 6-23).
This increase in suspended sediments may be because of bottom scour. As
in most cases, conductivity increased downstream from the quarry out-
fall. As a measure of nutrient level, both phosphates and nitrates of
the outfall and receiving stream were measured. In both cases of phosphate
and nitrate, the limestone quarry effluents were lower than the creek
and significantly lowered levels of both nutrients in the creek.
Very little plankton was found at the site, composed mainly of
Tabellaria sp., Navicula sp., Pleurosigma sp., and Qscillatoria sp. The
blue-green alga Qscillatoria was the dominant form.
The upstream invertebrates consisted of bloodworm larvae (Tendipes
sp.), Limnephi1 id caddis fly larvae and the clam Unio sp. Downstream
invertebrates were characterized by a similar fauna with the addition of
mosquito larvae (Culex sp.)
6.2.10 Flintkote Stone Products, 24 July 1980
On this date, Goodwin Run was turbid because of a recent rain.
Total suspended solids ranged from 9.0 mg/1 to 10
6-37
-------
TABLE 6-23. FRANCE STONE COMPANY
BLOOMVILLE, OHIO
JULY 23, 1980
RECEIVING STREAM - EICHOLTZ DITCH
Station
Depth
(meters)
Temperature
('Centigrade)
Conductivity
(mmhos/cm)
Dissolved
Oxygen
(ppm)
pH
ORP
(mv)
Total
Suspended Phosphates
Solids1*s (mg/liter)
(mg/1) Total Ortho
Nitrates
(mg/liter)
o\
I
CjO
00
Highway 8 Bridge
upstream of discharge
Highway A Bridge
upstream of discharge
Highway 58 Bridge
upstream of discharge
Highway 23 Bridge
upstream of discharge
Highway 77 Bridge
upstream of discharge
Quarry Pit
Upstream from Outfall
Outfall
Mixing Zone down-
stream of discharge
Downstream of mixing
zone
Highway 49 Bridge
downstream of dis-
charge
0.4
0.4
0.4
0.2
0.0
0.3
0.2
0.5
0.4
0.5
Gravimetric method
2Hack method (photometric)
'Sample destroyed
20.2
21.4
21.1
21.2
28.5
21.8
20.0
21.8
21.7
21.0
0.28
0.32
0.34
0.32
0.83
0.32
0.89
0.34
0.40
0.41
3.12
5.48
5.65
5.91
7.98
6.06
8.45
6.18
6.52
6.20
—intermittent pools
6.53 169
6.95
3.13
7.28
8.36
7.33
7.90
7.38
7.43
7.60
265
276
282
274
239
091
233
199
292
65
5.01
751
761
.44
.11
.22
.37
.15
<.01
.04
12
4.0
5.1
9.9
-------
mg/£, an insignificant increase as the creek passed the quarry
(Table 6-24). Conductivity in Goodwin Run was increased by the
quarry discharge from a value of 0,24 mmhos/cm above the quarry
to 0.70 mmhos/cm below the quarry. Phosphates and nitrates in
the creek were measured to determine if the quarry was adding to
the nutrient load of the creek. There was a significant increase
in nitrates in Goodwin Run below the quarry; which was unexplained.
Possibly there were unnoticed sanitary loadings.
The plankton of the creek were characteristic of mildly
eutrophic conditions, dominated by blue-green algae (Arthrospira
sp., and Oscillatoria sp.), volvocalean green alga (Pandorina sp.)
and euglenoids (Phacus sp.). The diatoms Tabellaria sp., Cymbella
sp., Navicula sp., Surirella sp., and Cocconeis sp. were also
found. The desmid Closterium sp. occurred in one downstream sam-
ple . Zooplankton was composed mainly of Ostracods and Tintinnids.
The dominant alga at downstream stations was the pollution-
tolerant green alga StigeocIonium sp.
Benthic fauna consisted of bloodworm larvae, Tendipes
sp.; clams Psidium sp.; and snails, Viviparous sp. Numerous
water striders, Gerris sp., were also found.
6-39
-------
TABLE 6-24. FLINTKOTE STONE PRODUCTS COMPANY, TEXAS QUARRY
COCKEYSVILLE, MARYLAND
JULY 24, 1980
RECEIVING STREAM - GOODWIN RUN
Station
Dissolved
Depth Temperature Conductivity Oxygen ORP
(meters) ("Centigrade) (nmhos/cm) (ppm) pU (mv)
Total
Suspended
Solids'
(mg/1)
Phosphates
(mg/llter)
Total Ortho
Nitrates
(mg/llter)
Goodwin Run up-
aCream from plane
0.2
26.5
0.24
8.86
8.88
262
9.0
Calclte Discharge
below discharge;
discharge not
active
0.0
25.2
0.20
8.18
8.43
267
11
Entrace to under-
ground portion of
stream
0.2
25.4
0.37
9.13
8.67
230
.
6-40
Outfall of under-
ground portion
of stream
Outlet of 880 pond
0.4
0.2
21.3
25.2
0.41
0.85
7.68
8.63
8.16
815.
239
259
13'
Goodwin Run below
last quarry dis-
charge
0.4
23.3
0.70
8.94
8.48
296
10
.17 <.01
.18 .03
2.9
2.6
<.01 <.01
8.7
^Gravimetric method
-------
7.0 EFFECTS OF DISCHARGES
7.1 Water Quality Effects
As reported in Section 6, water quality samples were collected
from limestone quarries and processing plants across the nation. These
samples were analyzed for suspended and dissolved solids, silica, hardness,
turbidity and pH. Concentrations of lead, mercury, nickel, chromium,
cadmium, selenium, zinc, and iron were also determined. In addition,
samples were collected and analyzed for asbestos.
The physical characteristics of the samples collected are
summarized in Table 6-2 by type of discharge (i.e., untreated washing
wastewater, sedimentation pond effluent, and pit dewatering discharges).
As reported in Section 6.1, water quality varied significantly at different
points within the process flow stream.
In this section, the water quality effects of each constituent
are discussed in general, followed by a discussion of the effects of
each constituent as found in limestone effluents in particular. The
discussion of general effects is essentially a literature review, and
effects of limestone effluents are evaluated based on information obtained
from this review.
The water quality effects of treated wastewater (sedimentation
pond effluents), untreated wastewater (washing wastewater before sedimentation),
and pit water are examined. The effects of untreated wastewater are
included in the discussion as a potential discharge, although such discharges
are not permitted by the National Pollution Discharge Elimination System
(NPOES). Practically all mines and washing operations now employ wastewater
treatment systems as a result of the NPDES requirements. The effects of
untreated wastewater were included in the study to determine the effect
of no NPDES requirements.
7-1
-------
These effects of untreated wastewater on receiving streams are
derived from the literature.
Water quality effects include both beneficial and detrimental
effects. In many instances, the discussion describes effects without
referring to them as either beneficial or detrimental, although some
beneficial and detrimental effects are noted.
7.1.1 Suspended Solids and Turbidity
General Effects
Total suspended solids (TSS) are the non-filterable residue
(particle sizes above 0.8 micron) remaining after evaporation at 103° to
105°C (APHA, 1976). Suspended solids may consist of either organic or
mineral matter. Mineral suspended solids, such as those found in limestone
wastewater, do not decompose and deplete the dissolved oxygen in the
stream, although they may cause other minor types of undesirable effects.
Turbidity is closely related to suspended solids and will
therefore be discussed in this section. Although there is not an exact
relationship, correlations have been observed between TSS and turbidity
(Oelfino, 1977). Turbidity is an expression of the optical properties
of water and depends on both the concentration and composition of particles
in the sample (A?HA, 1976).
Suspended solids settling from the water column can blanket
the streambed causing harm to benthic organisms. This problem, as well
as the effects of solids in the water column on fish and wildlife, will
be discussed in Section 7.2 on Biology.
7-2
-------
Suspended solids adsorb and transport other constituents such
as pesticides and nutrients (NAS, 1972; Robinson, 1971; Brashier, 1973;
Klages, 1974). Agricultural lands are a major source of suspended sol ids
in the form of sediment runoff, and pesticides and nutrients are generally
associated with this source of sediment runoff.
Suspended solids interfere with domestic water supplies. The
need to remove the suspended solids results in increased treatment costs.
Turbidity, which is indirectly related to suspended solids concentrations,
is limited in water supplies by the National Interim Primary Drinking
Water Regulations to a maximum monthly average of one turbidity unit.
This limit for turbidity is not only desirable for clarity of the drinking
water, but is also desirable because suspended solids decrease the effective
ness of disinfectants by protecting organisms from proper contact with
the disinfectant (Metcalf and Eddy, Inc., 1979).
Suspended solids in industrial water supplies also require
costly treatment. Suspended solids and turbidity must be limited not
only in consumptive products (beverages, food products, ice), but in
other industrial processes such as boiler feed, cooling water, pulp and
paper, textiles, petroleum refining, and tanning (NAS, 1972). Table 7-1
presents water quality characteristics of water which have been used as
sources for industrial water supplies.
7-3
-------
TABLE 7-1. SUMMARY OF SPECIFIC DUALITY CHARACTERISTICS OF SURFACE WATERS THAT
HAVE BEEN USED AS SOURCES FOR INDUSTRIAL WATER SUPPLIES (Unless
otherwise indicated, units are mg/1 and values are maximums. No
one water will have all the maximum values shown.)
lollar Makeup UiUr
Coollag Hater
Proctai Uatar
1
Character1stlea
lidiMtrUl
0 to 1,500
pslg
Utility 700
to 5,000
MU
ickUb*
Through
Nakaup
IkjtcU
Through
Textile
Industry
Bacycle SIC-22
Induat ry
SIC-24
Pulp and
Paper
Indutrr
SlC-26
150
3
600
1,400
19,000
600
680
600
SO
35,000
15,000
5,000
500
1,000
Silica (StO|) 150
Alualnus (Al) 3
Icon (Fa) 80
Hangaaaaa Ofti) 10
Copper (Cu)
Calelw (Ca)
Hagnealua (Mg)
Sodlus & potaaalw
(»a+*)
Aaonia (MM,)
Bicarbonate (BCO,) 600
Sulfate (SO,) 1,400
Chloride (CI) 19.000
Pluorld* (V)
Nitrate (K>») ......
Phosphate (PO*)
DliieUtd SolUi 35,000
Sua pe od ad Sollda 15,000
Hardaaaa (CaCO,) 5,000
Alkalinity (CaCO,) 500
Acidity (CaCO,) 1,000
pM, unite
Color, ualta 1,200
Organica: .
Methylene blue ac- 2
tlva subatances
Carbon tetrachloride 100
extract
Chealcal oxygen da- 100
•and (COO)
Hydrogaa aulflde (HzS)
Teaperatura, P 120
fwater coatalalDg la exceaa of 1,000 ag/1 dlaaolvad aollda.
Slay ba £1,000 (or aechaalcal pulping operatlona.
Jilo particles >3 am dlaaater.
Ona i|/l for praaaurea above 700 palg.
*No floerlrf oil.
Appllaa to bleached chaalcal pulp and papar only.
*12,000 ag/1 Fe Includes 6,000 F«+; and 6,000 Fe".
*STH Standards 197" or Standard Methods 1971.
Source: Water Quality Criteria, 1972.
600
680
500
180
2,700
22,000
180
2,700
22.000
1,200
30
4
1,000
5,000
850
500
0
5.0-8.9
100
500
30
4
1,000
15,000
850
500
200
3.5-9.1
1,200
1.3
100
100
35,000
250
7,000
150
0
5.0-8.4
1.3
100
200
50
150
25
25
14
80
1.0
1.0
0.3
2.5
10
0.02
0.02
1.0
500
500
1,200
1,200
35,000
250
7,000
150
0
5.0-8.4
150
1,000
120
1,080
475
4.6-9.4
J60
Chemical
Industry
SIC-28
2
250
600
8S0
2,500
10,000
1,000
Petroleoa
Industry
SIC-29
Irla.
Hatala
Industry
SIC-33
(Ualag Industry
Copper
Sulfide
Concentra-
tor Proceas
Hater
011 Ucovery
Injection Haters
40
480
900
1,600
1.2
3,500
5,000
1,510
(CaCOa)
1,500
3,000
1,000
200
75
3-9
1,530
415
12,000
12,000* 0.2
400 2,727
12,000 1,272 655
10,840 42,000
142 281
64,000 2,560 42
18,980 72,782
34,292 118,524
Reproduced from
best available copy.
-------
When suspended solids concentration and turbidity are
high, recreational uses of water bodies are impacted. Swimming
and diving become hazardous when visibility in the water is re-
duced, and the aesthetic attractiveness of water also decreases.
When fish and wildlife are impacted (Section 7.2), non-contact
recreation such as fishing is likewise effected.
Another effect of suspended solids m natural waters
is the physical effect upon channels and impoundments,- although
such effects are caused primarily by sediment runoff and trans-
port. Settling of solids causes aggradation of streambeds and
filling of impoundments which results in interference with navi-
gation, increased flooding, and loss of storage capacity (Univer-
sity of Pittsburgh, 1972). In certain cases, costly dredging is
required to improve such conditions. Lakes and impoundments may
also have an increased eutrophication potential due to nutrients
associated with suspended solids which are entering the lake.
TSS and Turbidity in Limestone Effluents
Total suspended solids (TSS) and turbidity varied con-
siderably between points within the process flow stream, specifi-
cally before and after sedimentation of stone washing wastewater.
Table 7-2 below summarizes the results for TSS and turbidity for
samples collected during this study. The effects of these two
types of wastewaters (treated and untreated) will be discussed
in this section.
The concentrations of suspended solids found in sedi-
mentation pond effluents and pit dewatering discharge should
have a minimal effect on water quality of receiving streams.
The suspended solids would tend to settle in the receiving stream,
but the settling rate is dependent on the velocity and turbulence
7-5
-------
TABLE 7-2. SUMMARY OF RESULTS OF TSS AND TURBIDITY ANALYSES
Type of Sample
TSS
(mg/1)
Range
Median
Turbidity
(FTU)
Range
Median
Sedimentation Fond
Effluent
<1 - 13.0
1-12
9.0
Pit Dewatering
Discharge
Untreated Washing
Wastewater
<1 - 62.0
3.7 <1 - 16
1.5
168 - 16,000 4,100.0 32 - >250 >250.0
of the stream, as well as the settling velocity of the particles.
After passing through sedimentation ponds, the effluent would
probably contain only the smaller, slower settling solids, which
would probably not settle immediately at the outfall point, but
would generally be more distributed in the downstream directions.
The turbidity levels in the sedimentation pond efflu-
ents and pit discharges are within the range of turbidities re-
ported for natural waters. Average turbidities in thirteen major
rivers across the United States ranged from 2.5 to 56.8 JTU in
1977 (CEQ, 1979). In addition, at four of the five quarries
visited where stream quality was available, TSS values in the
receiving streams upstream of the discharge points were higher
than the TSS values in the sedimentation pond effluents and pit
discharges.
Therefore, since effluents were at or below concentra-
tions of TSS found in natural water, sedimentation pond and pit
dewatering discharges generally should not cause cost increases
7-6
-------
to municipalities treating water to reduce suspended solids
and turbidity for public water supplies.
Similarly, low levels of TSS and turbidity from sedi-
mentation ponds and pits would probably not effect industrial,
agricultural or recreational water uses, since the effluent con-
centrations are within the range of typical concentrations of
natural water.
The concentrations of suspended solids found in wash-
ing wastewater before entering sedimentation ponds would have a
significant effect on receiving stream water quality if dis-
charged without further treatment, although such discharges cur-
rently are not permitted. At the TSS and turbidity levels sum-
marized in Table 7-2 for untreated washing wastewater, the phy-
sical effects on the streambed, pools, or impoundments would be
more pronounced than for sedimentation pond effluent. The ef-
fects on various water users would be unacceptable in many cases.
If untreated washing wastewater were discharged di-
rectly to a receiving stream, a large percentage of the sus-
pended solids would settle to the streambed immediately down-
stream of the discharge point. The first pool below the out-
fall would function essentially as a sedimentation pond for sus-
pended solids remaining in the water at that point. Detrimental
effects to the biological communities resulting from such condi-
tions are discussed in Section 7.2. Other effects include loss
of channel capacity and impoundment storage and the resuspension
of solids during high flow events (Delfino, 1977).
The extent to which water uses would be effected by
a discharge of untreated suspended solids would depend on factors
such as the amount of dilution provided by the receiving stream,
the distance of the desired use downstream of the discharge point,
and the type of water use being considered.
7-7
-------
In cases where a stream is a source of a water supply
for either municipal or industrial uses, it is generally implied
that there is sufficient flow to provide dilution of a lime-
stone process wastewater discharged to that stream. Also, since
suspended solids would tend to settle in the stream, the effect
of suspended solids would be decreasing in the downstream direc-
tion. Therefore, the effect on water supplies of a discharge of
suspended solids would probably be less significant than the
physical impacts to the stream near the discharge point. How-
ever, the potential exists for water supplies to be effected if
they are located near the point of discharge of untreated lime-
stone wastewaters and during high flow periods when the settled
solids could be resuspended.
Suspended solids concentrations in untreated limestone
process wastewaters could potentially effect agricultural water
uses, depending on the proximity to the discharge point and the
amount of dilution provided by the receiving stream. Soils ir-
rigated with high TSS waters could be effected by the formation
of a surface layer, which could reduce infiltration and decrease
soil aeration (NAS, 1972). Leafy crops could be coated with a
silty film making them less marketable. In addition, irrigation
water storage ponds and stock watering tanks downstream of a
limestone discharge could be filled with sediment much more rap-
idly than under natural conditions.
Finally, recreation areas located downstream of a dis-
charge of untreated process wastewater would probably become less
attractive and desirable because of streambed aggradation and pool
sedimentation.
7-8
-------
7.1.2 Dissolved Solids
General Effects
Total dissolved solids (TDS) are the remaining residue
upon evaporation of a filtered sample at 103 to 105°C. Dis-
solved solids consist mainly of inorganic salts, small amounts
of organic matter, and dissolved gases (APHA, 1976).
High levels of TDS are objectionable primarily in
municipal and irrigation water supplies. The National Secondary
Drinking Water Regulations established a limit of 500 nig/1 of
total dissolved solids for public water systems. Objectionable
tastes increase with increasing concentrations of TDS, and, for
high levels of TDS, there may be a laxative effect, particularly
upon transients. High concentrations of mineral salts (particu-
larly sulfate and chloride) are associated with costly corrosion
damage in water systems (NAS, 1972).
Dissolved solids can reduce productivity and have a
detrimental effect on crops at high levels. Table 7-3 describes
the effects of TDS at various levels.
TABLE 7-3. RECOMMENDED GUIDELINES FOR SALINITY
IN IRRIGATION HATER
Classification
TDS mg/1
Water for which no detrimental effects are
usually noticed
500
Water that can have detrimental effects on
sensitive crops
500-1,000
Water than can have adverse effects on many crops; requires
careful management practices
1,000-2,000
Water that can be used for tolerant plants
with careful management practices
on permeable soils
2,000-5,000
Source: Water Quality Criteria, 1972, National Academy of Sciences,
National Academy of Engineering
7-9
-------
Water used as a supply for livestock can create prob-
lems and, at very high levels, be completely unsuitable for use
as stock water (NAS, 1972). Table 7-4 summarizes the guidelines
for use of saline waters for livestock watering.
Industrial and commercial water supplies may be ef-
fected by dissolved solids, depending on the process and product.
Table 7-1 (presented previously) includes dissolved solids con-
centrations which have been used by various industries.
T «¦"» n I Tl inn /¦* I /I C /*% 1 1 J « 1 m T •% ann /-* /% T? XT JC 1 <• •*» n
lULdli UlbwUlVvU IjUX LQp xil L i TT*" 3 UOilc HiX X JL ucU t-S
The following table summarizes the concentrations of
TDS at various points in the process flow stream at limestone
processing plants.
TABLE 7-5. SUMMARY OF RESULTS OF TDS ANALYSES
TDS
mg/1
Type of Sample
Range
Median
Sedimentation Pond Effluent
223
467
299
Pit Dewatering Discharge
231
- 1,800
613
Untreated Washing Wastewater
397
- 9,600
490
The TDS concentrations in the effluents from sedimen-
tation ponds sampled is less than the drinking water standards
(500 mg/1), and is at excellent levels for agriculture and most
industrial uses.
7-10
-------
f»AT*T TT 7 /, HTTTTW TH TUP ITCTT AH1 CATTMTT TJATTTB C TAD
TAdLci /-4. oUiuUi iu inlL Uot Ur bAL.lNr- WAiiiKb rUK
LIVESTOCK AND POULTRY
Total Soluble Salts
Content of Waters
(mg/1) Comment
Less than 1,000 Relatively low level of salinity. Excellent for all
classes of livestock and poultry.
1,000- 2,999 Very satisfactory for all classes of livestock and
poultry. May cause temporary and mild diarrhea in
livestock not accustomed to them or watery droppings
in poultry.
3,000- 4,999 Satisfactory for livestock, but may cause temporary
diarrhea or be refused at first by animals not ac-
customed to them. Poor waters for poultry, often
causing water feces, increased mortality, and de-
creased growth, especially in turkeys.
5,000- 6,999 Can be used with reasonable safety for dairy and beef
cattle, for sheep, swine, and horses. Avoid use for
pregnant or lactatlug animals. Not acceptable for
poultry.
7,000-10,000 Unfit for poultry and probably for swine. Consider-
able risk in using for pregnant or lactating cows,
horses, or sheep, or for the young of these species.
In general, use should be avoided although older
ruminants, horses, poultry, and swine may subsist on
than under certain, conditions.
Over 10,000 Risks with these highly saline waters are so great
that they cannot be recommended for use under any con-
ditions
Source: Water Quality Criteria, 1972, National Academy of Sciences,
National Academy of Engineering
7-11
-------
Several of the pit dewatering discharges sampled con-
tained TDS concentration above the drinking water standard. The
median value observed was 613 mg/1. The pit water is primarily
made up of ground-water seepage into the pit and the TDS levels
observed are probably the natural ground-water quality.
The TDS concentrations reached very high levels in the
untreated washing wastewater at one facility visited. However,
the median value for all samples was below the drinking water
standard of 500 mg/I. The potential effects of these levels de-
pend to a great extent upon the amount and quality of dilution
water in the receiving streams. Where there is even a small
amount of dilution available, water users should not be signifi-
cantly effected by the levels of TDS measured at these limestone
facilities.
7.1.3 Hardness
General Effects
Hardness is the sum of the polyvalent cations and is
usually expressed as the equivalent quantity of calcium carbo-
nate. The most common cations of hardness are calcium and mag-
nesium. In general, these ions in public water supply sources
are not cause for concern to health, although there are some
indications that hardness may effect the tolerance of some or-
ganisms to other metal ions (NAS, 1972).
Hardness is of concern in domestic and industrial wa-
ter supplies because of the buildup of scale deposits when the
water is heated. Refer to Table 7-1 for hardness levels which
have been used in various industrial categories.
7-12
-------
Hardness in Limestone Effluents
The concentrations of hardness found in the various
limestone quarry and processing plant flow streams are sum-
marized in Table 7-6.
TABLE 7-6. SUMMARY OF RESULTS OF HARDNESS ANALYSES
Hardness
(mg/1 as CaCOa)
Range Median
Sedimentation Pond Effluent
158 -
264
219
Pit Dewatering Discharge
150 -
1,272
435
Untreated Washing Wastewater
220 -
1,500
950
The sedimentation pond and pit dewatering discharges
contained low to medium levels of hardness. Depending on the
site-specific characteristics of receiving streams, these levels
would not cause major problems for water users, since water
sources for most users would consist of significantly higher
streamflows than the wastewater discharge rate. The higher
streamflows will provide large amounts of dilution to a given
G.I>9 ClloXgiv D 6 X OX & cL WciLcL Ubc JLs vilCr Uull L 6 ~ V C tor • JT\. W J* I ^!!!r %¦* JL> *iir- * -L» i3 j -I— (¦» JL* *21 11 ly,*
7-13
-------
likely that domestic or industrial water users would encounter
buildups of scale deposits in their water systems.
7.1.4 Silica
General Effects
Silica or silicon dioxide (Si02) occurs naturally es-
pecially as quartz and agate and is also found as the cementing
agent in sedimentary rocks such as sandstone. Silica ranks
next to oxygen in abundance in the earth's crust, and degrada-
tion of silica containing rocks results in the presence of
silica in natural waters.
The silica content of natural water is most commonly
in the 1-30 mg/1 range although concentrations as high as 100
mg/1 are not unusual. Concentrations exceeding 1,000 mg/1 are
found in some brackish waters and brines (APHA, 1976).
For some industrial users, high levels of silica in
water is undesirable because it forms a scale on equipment.
Table 7-1 includes levels of silica in waters which have been
used by various industries.
Silica in Limestone Effluents
The levels of silica measured in samples collected at
limestone quarries were uniformly low, regardless of the type of
process being sampled. Table 7-7 summarizes the results for
silica.
7-14
-------
TABLE 7-7. SUMMARY OF RESULTS OF SILICA ANALYSES
Silica
(mg/1 as Si£>2)
Type of Sample
Range
Median
Sedimentation Pond Effluent
0.8 - 8.5 .
3.3
Pit Dewatering Discharge
0.6 - 11.0
4.8
Untreated Washing Wastewater
0.9 - 9.0
6.6
These levels of silica are in the range of silica con-
centrations for natural waters and should not result in detri-
mental effects for water users.
7.1-5 £H
General Effects
The National Secondary Drinking Water Regulations set
a range of 6.5 to 8.5 for public water supplies. Waters with pH
values outside that range have a higher probability of corrosive
action.
pH in Limestone Effluents
The range of pH for all samples taken at limestone
quarries and processing plants was 7.34-8.30. These levels of
pH are nearly optimum for all uses, including municipal, indus-
trial, and irrigation water supplies and for recreational uses.
No treatment for pH adjustment was observed.
7-15
-------
A potential beneficial effect of limestone effluents is the
buffering capacity, especially in streams impacted by acid mine drainage
or acid rain. Limestone quarry discharges would tend to neutralize
waters with a low pHr although the degree of neutralization would depend
¦v .
on the dilution ratio of the discharge flow to the stream flow and the
buffering capacity of the particular discharge.
7.1.6 Heavy Metals
General Effects
The heavy metals which were analyzed are important water quality
parameters due to toxicity and objectionable taste, lead, mercury,
nickel, chromium, cadmium and selenium are all toxic to humans above
certain levels. These metals, with the exception of nickel, have been
limited to specific maximum concentrations in public water supply system
by the National Interim Primary Drinking Water Regulations because of
their toxicity. Nickel has had limits recommended for protection of
freshwater and marine aquatic life (MAS, 1972).
Undissolved zinc and iron and generally considered nontoxic,
but result in objectionable tastes, and iron can stain plumbing fixtures,
spot laundry, and accumulate as a deposit in distribution systems (NAS,
1972). Zinc is toxic in solution, and is persistent in sediments. Zinc
and iron are included in the National Secondary Drinking Water Regulations
because of these undesirable characteristics.
Table 7-8 presents the recommended water quality criteria for
the metals which are included in this study.
7-16
-------
TABLE 7-8. WATER QUALITY CRITERIA FOR HEAVY METALS
Metal Criteria Basis for Inclusion
(mg/1) in Quality Criteria
lead
mercury
chromium
cadmium
selenium
.050
.002
.050
.010
.010
toxicity
toxicity
toxicity
toxicity
toxicity
zinc
iron
5.000
.300
taste
taste, nuisance
nickel
.002
>.100
minimal risk to organisms
hazard to marine organisms
Source: Water Quality Criteria, 1972
EPA-R3-73-033, March 1973
7-17
-------
Heavy Metals in Limestone Effluents
As discussed in Section 6.1, the metals concentrations
in the various limestone effluents are relatively low. The ef-
fects of the heavy metals concentrations measured, especially in
sedimentation pond and pit discharges, should not have a signifi-
cant effect on the water quality of receiving streams or down-
stream uses. Refer to Table 6-11 for a summary of the heavy
metals analyses results. The concentrations of all metals ex-
cept lead are below the drinking water standards in the efflu-
ents from sedimentation ponds and pit discharges. The results
of the lead analyses are questionable since the dissolved con-
centration is greater than the total concentration for the same
sample, and that sample is the one concentration of lead which
is higher than the drinking water standard.
For samples taken from washing wastewater prior to
sedimentation treatment, the dissolved metals concentrations
were all less than the drinking water standards (or the 0.1 mg/1
criteria for nickel). The maximum total metals concentrations
were noteaoiy tiigner tnan trie dissolved metals ror lead, nickel,
chromium, zinc and iron. The total concentrations of lead,
nickel, chromium and iron were approximately three, two, three
and 270 times their criterion, respectively, using the worst
case. Although the maximum total iron concentration of 81.0
mg/1 is 270 times the drinking water standard of 0.3 mg/1, this
standard applies only to the soluble iron, and the maximum dis-
solved iron concentration in limestone effluents is <.1 mg/1.
The total concentrations of the remaining metals (mercury,
cadmium, selenium, and zinc) were less than the drinking water
standards.
It is noteworthy that the only concentrations above
the criteria for the metals were found in the particulate phase
7-18
-------
of the untreated washing wastewater. It is evident that these
particulates settle during treatment (sedimentation) and that
concentrations have decreased significantly in the sedimentation
pond effluent samples.
7.1.7 Asbestos
General Effects
"Asbestos" is a generic term used for the fibrous form
of a number of minerals. The mineral groups, mineral names, and
chemical compositions are given below:
Group
Serpentive
Amphibole
Name
Chrysotile
Anthophyllite
Amosite
Crocidolite
Tremolite
Chemical Formula
3Mg0-2Si02-2H20
(MgFe)7Si8022(0H)2
(Fe)7Sig022(OH)2
NaFe8(Si03)2 «FeSi03¦
Ca2Mg5Si8022(0H)2
H,0
Asbestos is fire resistant, flexible, and has very
high tensile strength for its weight. Because of these attri-
butes it has many industrial uses such as reinforced cement pipe
and fireproof insulation. The chrysotile form has longer, more
flexible fibers and is the most commonly used form.
There is substantial evidence that airborne asbestos
is a carcinogen. Asbestos workers, as a group, suffer increased
rates of cancer of the esophagus, stomach, colon, and peritoneum,
as well as increased incidence of lung disease. The implication
is that the inhaled asbestos is cleared from the lungs by mucous
removal apparatus, then swallowed, and once in the gastro-intesti-
nal tract, the asbestos fibers induce tumors (Kuschner, 1974).
7-19
-------
In non-occupational exposure, however, the health effect of long term
low level exposure is largely unknown.
The EPA is required by law to publish criteria for water quality
for 65 pollutants with the protection of aquatic life and human health.
The criterion for asbestos states: "For the maximum protection*of human
health from the potential carcinogenic effects due to exposure of asbestos
through ingestion of contaminated water and contaminated aquatic organisms,
the ambient water concentrations should be zero based on the non-threshold
assumption for this chemical. However, zero level may not be attainable
at the present time." (EPA, Ambient Water Quality Criteria, PB81-117335).
Asbestos occurs naturally in many areas throughout the United States,
and one would expect to find some asbestos in the water in those areas.
In addition, about 200,000 miles of asbestos reinforced cement pipe are
in service in the United States (Olson, 1974), much of it carrying drinking
supply water. Finally, asbestos fibers have been used until recently in
the manufacturing of filter material for the beverage industry. Even
though asbestos is a carcinogen for which the EPA is obliged to recommend
zero level water concentrations, its ubiquitous occurrence in the human
environment will probably prevent that criteria from ever being achieved.
Common water treatment practices like sedimentation basins for
effluents, and polelectrolyte coagulation followed by filtration for
drinking water supplies can reduce asbestos concentrations substantially.
The flocculation, sedimentation, and filtration process used at the
Chicago Water Filtration Plants removed from seventy to ninety percent
of the asbestos fibers present in the raw water of Lake Michigan (McMillan,
1977).
7-20
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Asbestos in Limestone Effluents
Concentrations of chyrsotile asbestos found in the
limestone mining process waters investigated varied from <0.07
million fibers per liter (mf/1) to 390 mf/1. In the cases where
higher concentrations of asbestos were found, treatment of that
water in sedimentation ponds substantially reduced the number of
asbestos fibers (see Table 6-12). In areas where asbestos occurs
in the bed rock or soil, asbestos concentrations in water can range
from 0,7 to 4. mf/1 (Kahle, 1980). Sedimentation basins can prob-
ably be used to achieve this level of asbestos in the effluents.
Removal beyond this level may require more sophisticated techniques.
7.2 Ecological Effects of Limestone Quarry Effluents
Effluents from limestone quarry operations may cause
significant impacts upon the turbidity, hardness, pH, sediment
thickness and type, and both nutrient, and toxicant levels in a
receiving body of water (Figure 7-1). The effluents contain
finely divided limestone, usually a mix of calcium and magne-
sium carbonates. The chemical constituents of limestone are
non-toxic to humans and most forms of higher animal life and
will be treated as such in this report. It is to be noted,
however, that certain restricted habitats occur in streams or
lakes which have a naturally low pH or are located in areas de-
pleted in calcium or magnesium. In these areas, introduction
of limestone quarry wastes could have a significant impact on
the native biota. However, most, if not all, limestone quarries
discharge into streams that arise adjacent to the quarry sites
in soils already appreciably influenced by the surrounding lime-
stone deposits. As such it is rare to find a quarry which dis-
charges into a system that would be adversely affected by the
chemical constituents of treated limestone effluents.
7-21
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[ TURBIDITYt ^
{ DEPTH
[DISSOLVED SOLIDS fj
INSOLATION
SUSPENDED SOLIDSf
*
LIGHT PENETRATION
NUTRIENT
STATUS
CURRENT VELOCITY 'fc \—
TEMPERATURE
DISSOLVED OXYGEN
SUBSTRATE
TOXICANTS
HARDNESS*
1
I"
jo
5
z
- - INTERACTION
— DIRECT EFFECTS
t PRIMARY EFFECT OF LIMESTONE QUARRY EFFLUENTS
* SECONDARY EFFECTS OF LIMESTONE QUARRY EFFLUENTS
Figure 7-1. Effects of Limestone Quarry Effluents Upon Aquatic Communities
-------
Limestone and limestone products such as lime can in-
crease the pH of a receiving stream. This change in pH can free
much of the phosphate found in bottom sediments causing an en-
richment of the overlying waters, increased primary productivity,
and a subsequent increase in fish yield. This effect has been
used by fish farmers for centuries to increase yields. The
same effect, however, can also free toxic substances in the
sediments and make them available to the aquatic biota. It may
also create a eutrophic condition because of the increased avail-
ability of plant nutrients. This may partially explain the sy-
nergistic effects noted by many researchers between some toxi-
cants and turbidity.
Nitrate levels of a receiving stream may also be af-
fected by limestone quarry operations. Ammonium nitrate is used
as a high explosive in most quarries. Improper storage or incom-
plete combustion of the compound could result in increased levels
of nitrates in surrounding streams. A. similar situation has been
found in coal mining in the Western United States in surface
mining operations in semi-arid areas. In most areas the levels
of ammonium nitrate from quarry operations are orders of magni-
tude less than the amount contributed by agricultural runoff.
Using proper management practices, this should not be a concern
in most limestone quarry operations.
The physical effects of the limestone quarry effluents
on the resident biota of the receiving stream which are related
to turbidity and sediment increases include:
• reduced primary productivity caused by de-
creased light penetration;
• siltation of spawning beds, redds, and nests
of fish causing reproductive failures;
7-23
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o reduction in viability of fish eggs caused by reduced
oxygen availability;
o restricted visibility which place those aquatic predators
which depend on visual cues at a disadvantage vis a vis
those predators which depend upon other cues;
o decrease in the number of available suitable benthic
invertebrate habitats;
o pathological changes in gill structure in both fish and
invertebrates (fusion of lamellae and thickening of
respiratory epithelium);
o reduced capability to regulate ionic balance in fishes
because of reduced capacity of the gills;
o increase in disease susceptibility in affected biota;
o reduction in feeding rate in filter feeders correlated
with an increase in the amount of energy expended by
those feeders per unit food; and
o species shifts in the benthic invertebrates and attached
algae (both macrophytic and periphytic) to more sediment
tolerant forms.
These effects are extrapolated from the literature pertaining to the
effect of suspended solids and turbidity and applied to limestone quarries.
We attempted on a small scale to verify these effects with sampling and
analyses.
7-24
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Most limestone quarries which discharge effluents are
located in the eastern United States near metropolitan centers
which serve as the market for their product. Receiving streams
in these areas are already impacted by a mixture of agricultural,
sanitary, industrial, and urban wastes and the effects of the
limestone effluents are overshadowed by the impacts of these
pre-existing stresses.
In a few of the cases examined in this study best
management practices could appreciably lower the suspended sedi-
ment load to the receiving stream. For example, proper convey-
ance of waste streams and proper design of outfall pipes could
cut sediment loads. Non-point source sediment washed from the
stock piles and yard should be controlled to reduce the sedi-
ment load of adjacent creeks. Diesel fuel and oil wastes from
trucks and heavy equipment can contribute to the effluents from
a quarry site and should be minimized.
7.2.1 Effects of Limestone Quarry Effluents on Fish
Limestone and limestone products are non-toxic to those
fish adapted to life in hard, alkaline waters. The main effects
of limestone quarry effluents on fish in most streams in the
eastern United States are caused by the increase in suspended
sediments and turbidity caused by the effluent. The National
Academy of Sciences (1973) , expanding on an idea proposed by
Tarzewell (1957), states that the "...effect of color and tur-
bidity should not change the compensation point* more than 10
percent from its seasonally established norm, nor should such a
change place more than 10 percent of the biomass of photosynthetic
organisms below the compensation point..." They also suggest that
*The compensation point is the depth at which the light level
exists needed to balance primary productivity (photosynthesis)
with respiration.
7-25
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aquatic communities should be protected if the maximum (maximum
in this case refers to the naturally occurring maximum in the re-
ceiving body of water) concentrations of suspended solids are
exceeded by artificial additions (Table 7-9).
TABLE 7-9. LEVELS OF PROTECTION VERSUS NATURAL SUSPENDED
SEDIMENT LOADS (After NAS, 1973)
Level of Protection Proposed
Natural Suspended Solids
Maximum Concentration
High level of protection
2 5 mg/liter
Moderate level of protection
80 mg/liter
Low level of protection
400 mg/liter
Very low level of protection
>400 mg/liter
Most streams in the study areas are exposed at present
to periods during high flow events when suspended solids exceed
400 mg/liter. As was proposed, the EPA criteria for suspended
solids and turbidity were established at a level that "...should
not reduce the depth of the compensation point for photosynthetic
activity by more than 10% from the seasonally established norm
for aquatic life." The EPA criteria are essentially those of the
NAS report with the major exception of the recommendation to rank
the sensitivity of the receiving water in accordance with natu-
rally occurring variation in suspended sediments and turbidity,
EIFAC (1965) found that for inert suspended solids in
European waters there is no evidence that concentration of sus-
pended solids less than 25 ppm have any harmful effects on fish-
eries. They also found that it should be possible to maintain
good or moderate fisheries in waters which normally contain 25
7-26
-------
to 80 ppm suspended solids (criterion b). Other factors being
equal, however, the yield of fish from such waters might be some-
what lower than from those in criterion (a) (<25 ppm). In addition,
waters normally containing from 80-400 ppm suspended solids
(criterion c) are unlikely to support good freshwater fisheries,
although fisheries may sometimes be found at the lower concentra-
tions within this range. Finally, EIFAC (1965) indicates that at
the best, only poor fisheries are likely to be found in waters
which normally contain more than 400 ppm suspended solids (cri-
terion d). Gammon (1970) states "Thus criterion (b), while it
may apply to the biota of continental Europe, may be too liberal
for populations in the U.S. Certainly at the ranges from about
50 to 80 ppm or nig/it it appears that significant biotic reduc-
tions will definitely occur."
Suspended sediments affect adults, eggs, alevins, and
fingerlings. The mode of action and levels of concern may vary
from life stage to life stage. The TSS levels currently dis-
charged by the limestone quarries in this study are at levels
which pose little threat to the existing ecology of the studied
receiving streams.
7.2.1.1 Effects on Adult Fish
Wallen (1951) in testing 380 fish (16 species) observed
behavioral changes at turbidities greater than 20,000 ppm and
noted that these effects could be offset somewhat by aeration and
movement of the fish. Apparently death in cases of turbidity in-
duced lethality is caused by anoxia and C02 retention caused by
clogging of the gills (Ellis, 1937). Ellis (1944) states that
suspended sediments may cause abrasions on the gills allowing
disease organisms and parasites to infect the fish. Herbert and
Merkens (1961) indicate that the suspended sediments cause fusion
of adjacent gill lamellae and a thickening of respiratory epithe-
lium in affected fish. Cairns (1968) adds that turbidities may
7-27
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interfere with gill mediated ammonia and urea excretion as well
as oxygen uptake, The oxygen data is based on experimental evi-
dence of Smith et al (1965), who noted, using wood particles as
the suspended sediment, that oxygen uptake suppression varied
as the type of wood used in the experiments varied. Nonetheless,
the movement of the gills and their condition is critical in
maintaining gill capillary circulation (Cairns, 1968).
Cordone and Kelley (1961) found that in fish exposed
to turbid water and toxic chemicals (copper and zinc), death oc-
curred more rapidly than in the group exposed to toxic water
alone. They postulate that the effect of the suspended sediments
on gill action was exacerbated by the presence of toxic chemicals.
In an attempt to define harmful levels of suspended
sediments, Herbert and Merkens (1961) exposed fish to kaolin or
diatomaceous earth suspensions. No difference was noted in the
response of the fish to these suspensions. In an experiment
measuring long term survivability, they found that 30 ppm caused
no observable effects, 90 ppm caused slight effects, while 270
rmm caused deaths No difference in srowth was found between
p VCi>U>i9v«U UwaUiiw * tlw uxx CilUC O-IJ. gi UW UU WCLO JU U Li.JLJ.Vjl UCUWCCu
the controls and experimental fish, which conflicts in some de-
gree with the field data outlined below.
Of the common game species in Table 7-10, only Pomoxis
annularis (white crappie) is tolerant to high turbidities. They
in fact enjoy a competitive advantage in turbid waters.
Salmonids as a group exhibit avoidance of turbid waters
when possible. Smith (1940) observed that King Salmon- avoided a
section of muddy water in the Yuba River in favor of the clear
tributaries. Although Benoit et al (1968) found that young sal-
mon could tolerate exposure to high concentrations of sediment
for up to 120 hours, Bachmann (1958) found that cutthroat trout
•j»jl _ _ /"• _ _i _ __ J — J _ _ J - _ — _ XT
did not reed at suspended sediment concentrations at a maximum or
7-28
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TABLE 7-10. THE EFFECTS OF SUSPENDED SEDIMENTS ON
ADULT FISH OF COMMON GAME SPECIES
Species
Effect
Reference
Lepotais cyanellus
(green sunfish)
Lepomls gulosus
(waraouth)
Lepomls microlophus
(redeared sunfish)
Lepomls macrochirus
(bluegill)
Lepomls megalotis
(longear sunfish)
Mlcropterls salmoldes
(largemouth bass)
PoTOnifis annularis
(white crappie)
• slow growth rate in
turbid waters
• turbidity (14-16 JTU's)
did not affect feeding
or attack behavior but
did affect the social
hierarchy and increased
scraping behavior
• growth slower in turbid
waters
• requires relatively
clear water
• growth slower in turbid
ponds
• growth slower in turbid
ponds
• intolerant of large
amounts of silt
• low K (condition index)
associated with tur-
bidity
• 14-16 JTU turbidity
decreased activity
and bass demonstrated
"coughing"
• very tolerant of turbid-
ity and siltation
• does not compete well
with bluegills, black
crappies or largemouth
bass in clear waters
Hastings and Cross, 1962
Heimstraw et al., 1969
Hubbell, 1966
Buck, 1956
Hastings and Cross, 1962
Shireaan, 1968
Buck, 1956
Raney, 1965
Morgan, 1958
Heimstra et al., 1969
Walberg, 1964
Trautman, 1957
7-29
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35 ppm, although they exhibited no outward signs of distress.
Campbell (1954) exposed rainbow trout fingerlings to 1,000-2,000
ppm for twenty days, In the control condition 9.5 percent of the
fingerlings died, while in the experimental condition 57 percent
died. Griffin (1938), working with cutthroat trout and king
salmon, found that both species survived and fed for thirty days
in water that averaged 360 to 600 ppm and peaked at 3,500 ppm.
Herbert and Richards (1963) investigated the status of brown trout
in a clear control river, a river that averaged 60 ppm suspended
clay solids and had stretches with 1,000 - 6,000 ppm. In that
section of river with 60 ppm suspended solids, there was no de-
tectable difference from the control river. In the section with
1,000 - 6,000 ppm the trout population was one-seventh of the
control.
Wallen (1951) also determined the average fatal turbidi-
ties for sixteen species of fish. These values ranged from 38,250
ppm for Ambloplites rupestris to 222,000 ppm for Ameiurus melas
(black bullhead).
From the above review it can be seen that adult fish
can temporarily withstand high levels of suspended sediment in
their environment. Mortality in the case of adult fish killed
by high sediment concentrations is due to gill clogging and
abrasion. Behavioural changes occur before lethal levels of
suspended solids are reached. Salmonids are more sensitive than
most other adult fish to suspended solids.
Adult fish in a natural situation are able to avoid the
effects of turbidity by migrating to a non-impacted area or by
seeking shelter in a non-turbid refugia. The more damaging as-
pects to the fish population in bodies of water with high levels
of turbidity are the reduction of food organisms (invertebrates,
algae, and plankton), and reduction in available nesting sites
either from siltation of gravel beds or through a reduction in
macrophytie vegetation.
-------
7.2.1.2 Effects on Fish Reproduction Behavior and Success
Limestone quarry effluents may adversely affect the
reproductive behavior of adults, viability of fish eggs, and the
survival of juvenile fish.
Sediments affect the reproductive behavior, eggs, and
juveniles of different species in different ways. For example
Gammon (1970) found that longear sunfish (Lepomis megalotis)
preferentially nested in a clear tributary of Deer Creek, rather
than in Deer Creek itself and inferred that nesting sites in
Deer Creek were abandoned as turbidity increased. Wolf (1950)
cites erosion of topsoil and increased turbidity as the main
reason for the disappearance of the Atlantic salmon from its
previous range in the Eastern United States.
Eggs are affected by the blanketing action of the
sediments produced by quarries. This blanketing action causes a
lowering of oxygen levels and a buildup of C02 levels near the
eggs. Harrison (1923), working with eyed eggs of sockeye salmon
(Table 7-11), found an increase in mortality in those eggs
exposed to sediments. Schubel et al (1974) demonstrated that
sediment additions of up to 500 mg/liter had no effect on the
eggs of yellow perch or striped bass, but that 1,000 mg/liter
lowered hatching success, Hobbs (1937), working on king salmon,
brown, and rainbow trouts correlated egg mortality with sediment
load. Most losses occurred before the eyeing stage was reached.
Cordone and Kelley (1961) , after reviewing the available litera-
ture, reached the conclusion that ..the effect of sediment upon
alevins and especially eggs of salmonids can be and probably often
is disastrous. Even moderate deposition is detrimental,"
Sediments can also adversely affect nesting site
availability and nesting habits in certain species. Bluegills
(Lepomis macrochirus) and pumpkinseeds (Lepomis gibbosus)
7-31
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TABLE 7-11. SUMMARY OF HARRISON'S (1923) DATA ON MORTALITY
OF SOCKEYE SALMON EGGS UNDER VARIOUS SEDIMENT
LOADS
Number of Number of
Eggs Planted Description of Nest Eggs Hatched
500 Gravel from size of pea to hickory 350
nut, some clean sand
500 Gravel as above with a %" coating of 325
silt
500 Fine gravel sand, and small amount of 200
clay in sand
500 Fine gravel and much clay or mud in 170
sand
500 Gravel from size of hickory nut to 420
walnut, very little sand, no clay
or top covering of silt
7-32
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prefer clean sand for nesting while Che warmouCh (Lepomis
gulosus) prefers to nest in the shelter of a stump or rooted
aquatic vegetation (Larimore, 1957). The dearth of rooted
aquatic vegetation in sediment loaded streams also may lower fry
survival rates by removing refuges, Male longear sunfish
(Lepomis meealotis) build nests in clean gravel (Huck and
^ > -MM...... 0
Gunning, 1967). Spotted bass (Micropterus punctulatus) prefer
mud bottoms or gravel bottoms for nesting sites (Howland, 1931).
Smallmouth bass (Micropterus dolomieu) prefer coarse rubble as
a nesting site substrate. Occasionally smallmouths will nest on
soft sediments after covering them with woody debris and clam
shells (Turner and MacCrimmon, 1970). Smallmouth nests are
usually located in areas of low current velocity (Surber, 1943),
T Q "i* rt> Am ai i t" n r\ *3i C <¦» f Mt /"> i ci a *31 l m/% 4 /i o i t t( i I a m « n e* t I 4"*
Largemouin Dass ^riicxupcsirxs s3Luioj.u.6s) will tioc ncSt on s-ljlu
bottoms (Robinson, 1961), preferring building nests on sand,
gravel, roots, or aquatic vegetation (Mraz et al., 1961). Often
largemouth nests are located near boulders or pilings (Hunsaker
and Crawford, 1964). White crappie (Pomoxis annularis), however,
often spawn in highly turbid water under tree roots or similar
sheltered areas (Morgan, 1954),
From the above review, it can be stated that sediments
can interfere with the reproductive success of most common
freshwater game fish, salmonids being the most sensitive. The
centrarchid population is generally affected by a lack of
suitable nesting places. The effects on both eggs and reproduc-
tive bahavior are species specific and a continued input of non-
lethal amounts of sediment into a receiving body of water could
cause shifts in species abundance and community structure.
7-33
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7.2.2 The Effects of Limestone Quarry Effluents on Benthic
Communities
The component of limestone quarry effluents most re-
sponsible for changes in the benthic community is sediment.
This stonedust can modify habitats, smother sensitive organisms,
and indirectly damage the benthic community by reducing avail-
able lieht to benthic plants and bv increasing the migration
rate of benthic invertebrates.
Benthic Invertebrates
Gammon (1970) reported on a four year study of the
effects of limestone quarry effluents upon stream biota and con-
cluded that light sediment inputs (less than 40 mg/liter) caused
a 25 percent reduction in macroinvertebrate density. Heavier
sediment loads (greater than 120 mg/liter) resulted in a 60%
reduction in macroinvertebrate population density. Gammon
also reported that most invertebrates responded to the sediment
load in a like degree and thus the (iversity of the system was
not affected. This second conclusion has been contradicted in
the literature from studies done in other locales (Chutter, 1969).
Sediment introductions in Gammon's study also increased the drift
rate of benthic invertebrates. As a summary, Gammon states that
"reduction in the standing crops of fish and macroinvertebrates
were detected in a short segment of stream which received a load
/•s an en ati Hi "1/"* O a1 1 o a T a frtA-y q qti wfl/? /4i i -i- *1 "**"1 «r
ojl suspended xiiUigciu.J-C ouiiub ui iiu muic tnau, d.iici uuXJ-ng luc
spring and winter less than, 40 mg/1 more than the normal concen-
tration during a part of each day. Suspended material as well as
settled sediment was responsible..."
Ellis (1931), commenting on the Mississippi, Tennessee,
and Ohio Rivers stated that freshwater mussel populations were
being decimated by smothering of the less resistant young mussels
7-34
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and by a drawdown in the oxygen content of bottom waters due to
a covering of organic wastes by sediments and the creation of
anoxic conditions. A combination of silting followed by flood-
ing reduced the bottom fauna to 7.3 organisms/ft2 as composed to
25.5 organisms/ft2 in an unaffected area.
The distance downstream that effects could be detected
vary from report to report (Table 7-12).
The effects of inorganic sediments on benthic inverte-
brates varies according to the type of organism and its habitat.
The type of bottom (rubble, gravel, sand, or mud) is of paramount
importance in determining the productivity of a stream. Rubble
bottoms allow the highest production and inorganic silt and mud
bottoms are the least productive. The lowest productivities
are found on bedrock or fine sand (Smith and Moyle, 1944). This
bottom effect has been noted many times in the literature. Cor-
done and Kelley (1961) summarize: "The fact that insects are
less abundant on sand bottoms than on gravel and less abundant
on gravel than on rubble, has been adequately reported. The
processes of erosion greatly increase the relative proportion
of finer materials in stream bottom, and of course the deposition
of mining debris or gravel plant waste accomplishes the same
thing in a more startling and accelerated fashion. To us, there
would appear to be adequate evidence that increasing the amount
of fine material in the bottom of streams will eventually result
in a declining bottom fauna."
7.2.3 Plankton, Periphyton, Macrophytes and Attached Algae
Zooplankton can be directly affected by sediments at
concentrations of 300-500 ppm due to clogging and overloading of
their filter-feeding apparatus and digestive organs (Stephan,
1953). Robertson (1957) determined that different suspended
7-35
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TABLE 7-12. DISTANCE DOWNSTREAM SEDIMENT INDUCED
EFFECTS COULD BE OBSERVED
Location
Type of
Operation
Effects
Author
Wynooche River,
Washington
Chehalis River,
Washington
Powder River,
Oregon
Seigel Creek,
Idaho
Cold Greek,
Trickee River,
California
Trout Stream,
Cotes du
Nord, France
Gravel 75% reduction in benthic inverte-
Washing brates at 200 yards to 0.3 miles
downstream, 85% reduction 1.7
miles downstream.
Gravel 90% reduction in bottom orga-
Washing nisms 100 yards below outfall.
34% reduction 4 miles downstream.
Normal 6 1/2 miles downstream.
Gold Almost complete absence of orga-
Dredge nisms for 15-20 miles downstream,
(However, 1 year after silt was
flushed from the river, the orga-
nisms returned in abundance.)
Dredge 1/4 mile downstream devoid of
organisms. At one mile there
was a 50% reduction.
Gravel Greater than 90% reduction at
Washing outfall. 75% reduction 10 miles
downstream
Sand Bottom fauna disappeared to 4
Washing kilometers downstream, where the
suspended sediment load fell to
29 ppm.
Ziebell and
Knox, 1957
Ziebell, 1957
Wilson, 1957
Casey, 1959
Cordone and
Pennoyer, 1960
Vivier (in
EIFAC, 1965)
7-36
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solids caused differing toxicities in Daphnia magna, and that
at low levels,inorganic sediments may increase the organism's
productive rate,
Phytoplankton growth can be reduced by the shading
effect of suspended sediments. King and Ball (1964) found a
61 percent reduction in primary production in a stream impacted
by sediments from highway construction. This reduction in pri-
mary production is followed by a reduction in secondary produc-
tion. A decrease in the amount of phytoplankton available in an
aquatic ecosystem will be reflected in a decrease in the number
of organisms dependent upon that phytoplankton as a food source.
Burris and Cooper (1977) compared turbidity and growth
of the diatom Melosira sp. in Grenada, Mississippi. This study
indicates that in the range of 15-90 ppm Si02 turbidity, Melosira
can grow well. Melosira reached a level of 300,000 cells/liter
while the water column had a turbidity of 52 ppm SiCh . The au-
thors state that turbidity stimulated the growth of plankton.
However, no causal relationship can be demonstrated based on
their data. Variations in temperature, nutrient levels, and
season were unaccounted for in the study. The conclusion that
can be drawn from the data is that Melosira can maintain a
healthy population while subjected to levels of turbidity less
than 90 ppm SiC>2.
Westlake (1966) states that in turbid waters the sub-
surface light at one meter depth can be reduced by a factor of
10"6 compared to surface levels.
The distribution of periphyton and attached algae are
affected both by the blanketing effects of sediment and by lack
of suitable substrates. Many species of diatoms and green
7-37
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algae require a solid surface on which to attach. When there is
no solid surface, these attached algae and periphyton cannot
exist.
The response or aquatic macropnytes to limestone
quarry effluents is somewhat more complex than that of plankton,
periphyton, or benthic invertebrates. In addition to the
physical effect or blanketing action of the sediments, there is
a physiological interaction. Some aquatic angiosperms are
capable of using the biocarbonate ion, HC01. These plants can
use the carbon of the biocarbonate ion for photosynthetic carbon
fixation as well as the carbon of the C02 molecule, as in normal
photosynthesis. Since in most natural water the HCO3 ion has a
greater abundance than C02, HCOf use during photosynthesis
confers a competitive advantage to the plant that uses it. Hard
water lakes of elevated pH and alkalinity offer these HCOf
utilizing plants a highly productive habitat. Hutchinson (1975)
summarized Moyle's (1945) classification of aquatic North
American angiosperms according to their tolerances for alkalinity
(Table 7-13). Another group of photosynthetic organisms charac-
teristic of hard waters are the Charophytes, Chara and Nitella.
Of the two, Chara is more characteristic of hard water. Lime-
stone quarries have a characteristic aquatic flora dominated by
masses of Chara.
Aquatic plants also vary in their resistance to
deposited sediments. Some, such as Isoetes sp., are intolerant
of sediment deposition and unable to grow in areas of rapid
sedimentation. Hutchinson (1975) uses the example of a small
English lake with Juncus bulbosus f. fluitans in areas of most
rapid sedementation, Nitella opaca in areas of less deposition,
anc* Isoetes lacustris in areas where the deposition was slight.
7-38
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TABLE 7-13. RANGE OF ALKALINITY, pH, SULFATE, AND TOTAL SALINITY FOR SOME
NORTH AMERICAN WATER PLANTS
Plant Groupings Alkalinity ,
by Habitat as HCO3 CO2 Salinity
Type Species (mg liter-1) pH (mg liter-1) (mg liter-1)
I. Low Dissolved Solids Group: alkalinity <60 mg HC07 liter-1, lowest pH _<7.0, sulfate _<10.0
0.0-4.5
0.5-6.0
0.0-3.0
n.d.
0.0-5.8
0.9-10.2
0.5-6.0
0.5-1.0
I_. macrospora**
Sparganium augusti-
follium
¦ " g
S. minimum
— 1 g
Najas gracillima
Nymphaea tetragona
Ranunculus trichophyl-
lus var. eradicatus
Callitriche hermaphro-
ditica4
' ¦ ¦— g
Elatlne minima
Myriophyllum alterni-
florum
M. farwelli3
~ '¦'¦¦¦' - -
M. tenellum
... g
Littorella americana
liter Moyle's soft-water subgroup
Isoetes braunii
Sparganium fluctuans
Potamogeton spirillus
Scirpus subterminalis
Eriocaulon septangulare
Lobelia dortmanna
Nuphar microphylla
N. rubrodisca
10-55
7.0-8.0
24-55
7.0-7.3
22-56
7.0-8.3
10-52
6.8-7.5
12-54
6.7-7.8
15-51
6.8-7.5
9-50
6.8-7.3
0.6-39
6.8-7.3
(Continued)
-------
TABLE 7-1^. RANGE OF ALKALINITY, pH, SULFATE, AND TOTAL SALINITY FOR SOME
NORTH AMERICAN WATER PLANTS (Continued)
Plant Groupings Alkalinity
by Habitat as HCO3 C02 Salinity
Type Species (mg liter-1) pH (mg liter-1) (mg liter-1)
II. Euytropic Intermediate Group: ranging from dilute (<15 mg HCO? liter-1) to fairly hard (<100
mg HCOJ liter -1) water; Moyle's soft-water subgroup 2, with some changes.
Lowest alkalinity <1 mg HCO!" liter -1; sulfate variable, often high
Potamogeton gramineus 0.6-186 7.0-8.5 0.0-17
Sagittaria latifolia 0.6-363 6.3-8.8 0.0-199
Eleocharis palustris 0.6-273 6.3-9.0 0.0-396
_E. palustris var. major 0.6-223 6.8-8.8 0.0-155
Phragmites australis 0.6-363 6.3-9.0 0.5-396
• Lowest alkalinity 9-15 mg HCO3 liter-1; sulfate usually low
Equisetum fluviatile 9-363 6.8-8.8 0.0-16
Potamogeton alpinus 15-141 7.0-8.6 0.5-4
.P. etihydrus 12-148 6.7-8.6 0.6-6
.P. praelongus 13-375 7.1-9.0 0.0-143
Glyceria borealis 10-229 6.8-8.8 0.5-17
Calla palustris3
Potentilla palustris3
Callitriche palustris3
Myriophyllus verticil-
latuma
P. obtusifolius3
Glyceria neogaea3
III. Hard-water Group: alkalinity always >15 mg HCO- liter-1.
Lowest alkalinity 15-30 mg HCOJ liter-1; sulfate <75 mg liter-1
Pontederia cordata 22-113 7.2-7.9 0-10
Potamogeton amplifolius 15-255 7.1-8.8 0-28
P^. natans 23-376 6.8-9.0 0-50
Sagittaria cristata 23-223 7.2-8.8 4-24
(Continued)
-------
TABLE 7-13. RANGE OF ALKALINITY, pH, SULFATE, AND TOTAL SALINITY FOR SOME
NORTH AMERICAN WATER PLANTS (Continued)
Plant Groupings
by Habitat
Type
Alkalinity
as HCO3
Species
(mg liter ')
pH
CO 2
(mg liter-1)
Salinity
(mg liter *)
Lowest alkalinity 15-30 mg HCO? liter-1; sulfate <600 mg liter
-1
Heteranthera dubia 28-299
Ceratophyllum demersum 28-458
Myriophyllum exal-
bescens 28-458
Utricularia vulgaris
var. americana 20-363
Elodea nuttallii 27-247
Nymphaea tuberosa 23-363
Nuphar variegata 9-268
Potamogeton zosteri-
formis 22-299
Najas flexilis 23-375
Sagittaria cuneata 24-458
Vallisneria americana 23-338
Eleocaris acicularis 23-458
Acorus calamus 24-247
As above but sulfate can be very high
Typha latifolia
Scirpus acutus
12-458
21-273
7.6-9.0
6.3-9.0
7.2-8.9
6.8-8.9
7.3-8.8
6.3-9.0
6.8-8.6
6.9-9.0
7.2-9.0
7.3-9.0
7.0-8.9
7.0-8.9
7.3-8.8
6.3-9.0
7.2-9.1
.-1
0-318
0-332
0-317
0-318
0-282
0-178
0-178
0-282
0-318
0-317
0-318
0-318
4-318
0-1296
0-1296
350-1465
458-1089
501
Lowest alkalinity, between 30 and 150 mg HCO3 liter ; sulfate <75 mg liter
87-458 7.7-8.8 1-62
-1
Potamogeton friesii
]?. gramineus f.
myriophyllum
Z.- Hinoensis
P_. robbinsii
P_. berchtoldii sub
puscillus
37-207
40-200
40-176
38-228
7.0-8.8
7.7-8.8
7.2-8.4
7.0-8.8
0-39
0-18
0-18
0-17
(Continued)
-------
TABLE 7-13. RANGE OF ALKALINITY, pH, SULFATE, AND TOTAL SALINITY FOR SOME
NORTH AMERICAN WATER PLANTS (Continued)
Plant Groupings
Alkalinity
d
by Habitat
as HCO3
C02
Salinity
Type Species
(mg liter-1)
PH
(mg liter-1)
(mg liter-1)
P. strictifolius^
39-321
7.4-9.0
1-62
Sagittaria rigida
40-363
7.4-8.8
0-62
Elodea canadensis
43-363
7.0-8.8
0-37
501
Lowest alkalinity >30 mg HCO3 liter 1; sulfate
<600 mg per
liter-1
Sparganium euycarpum
43-460
7.2-8.8
2-199
Potamogeton foliosus
45-279
7.2-8.8
0-282
458-1431
P. nodosus
49-380
7.3-8.8
5-199
P. richardsonii
38-451
7.0-9.1
0-318
Najas guadalupensis
92-195
7.2-8.6
36-177
Alisma triviale
39-364
7.3-8.5
5-199
Leerisa oryzoides
37-338
7.2-9.0
0-178
Zizania aquatica
46-364
7.2-8.6
3-282
Scirpus heterochaetus
50-243
7.3-8.6
12-282
Lemna minor
50-320
6.3-9.0
0-254
Lemna trisulca
50-363
7.2-8.8
0-332
Wolffia colurabiana
104-268
7.2-8.4
20-178
Polygonum coccineum
91-253
7.7-8.8
16-178
P. natans
37-317
7.7-8.8
3-282
Hippuris vulgaris
37-362
6.8-8.8
0.5-199
As above but sulfate can be very
high
Potamogeton pectinatus
39-458
6.3-9.0
0.5-1297
350-35,873
Zannichelia palustria
var. maj or
92-412
7.6-9.0
8-1297
458-1465
Scirpus fluviatilis
37-268
7.0-9.1
0.5-630
S. americanus
107-338
7.4-8.9
3-1296
Spirodela polyrhiza
60-363
6.3-8.8
1-619
(Continued)
-------
TABLE 7-13. RANGE OF ALKALINITY, pH, SULFATE, AND TOTAL SALINITY FOR SOME
NORTH AMERICAN WATER PLANTS (Continued)
Plant Groupings
by Habitat
Type
Species
Alkalinity
as HCOl
(mg liter-1)
PH
C02
(mg liter-1)
Salinity
(mg liter-1)
IV. Alkali Water Group: in water with at least 150 mg HCO3 liter
erances usually much higher, Moyle's alkali water group
,c
-1
and 50 mg sulfate liter 1, tol
Ruppia maritima
Najas marina
Scirpus paludosus
179-458
179-458
179-241
8.1-9.0
8.2-9.0
8.4-9.0
50-396
50-1297
254-395
457-77,386
624-1089
Species for which there are Inadequate data, but most likely are In Group I.
^Including var rutiolides as well as typical var. strictifolius.
Moyle's records sub R. occidentalls, which Is usually not regarded as distinct from R. maritima.
Salinity ranges from Metcalf, 1931.
Source: Moyle, 1945; personal observation.
-------
In summary, aquatic macrophytes can be greatly ef-
fected by both sediment deposition from limestone quarry efflu-
ents and by the alkalinity and high pH associated with those
effluents. As was stated earlier, however, since most limestone
quarries are located in areas of the United States in which there
are extensive limestone deposits, it is expected that the vege-
tation present would already be adapted to that type of
environment.
7-44
-------
8.0
8.1
TREATMENT TECHNOLOGIES
Description of Treatment Technologies
Treatment of limestone quarry wastewaters consists
mainly of suspended solids removal. Major technologies employed
include settling ponds, flocculation followed by settling, clar-
ifiers, screens and filters. Of these, settling ponds are by
far the most used with 95-97% of treatment facilities using this
method. Flocculation and clarifiers are employed at 2-57° of
existing facilities and screens and filters are rarely required
(EPA, 1976).
8.1.1 Settling Ponds
The versatility, ease of construction and relatively
low cost, explains the wide application of settling ponds
compared to other technologies. The performance of these ponds
depends primarily on the settling characteristics of the sus-
pended solids, the flow rate through the pond and the pond size.
Settling ponds can be used over a wide range of suspended solids
levels. Often a series of ponds is used, with the first collec-
ting the heavy load of easily settled material and the others
providing additional solids removal to achieve the desired sus-
pended solids level. As the ponds fill with solids they can be
dredged to remove these solids or they may be left filled and
new ponds provided. The choice often depends on whether land
for additional new ponds is available. When suspended solids
levels are low and ponds large, settled solids build up so
slowly that neither dredging nor pond abandonment is necessary
for a period of many years.
8-1
-------
In many cases, settling is a preliminary step in the
recycle of water for washing purposes. The level of suspended
solids commonly viewed as acceptable in recycled water used for
construction materials washing is 200 mg/l and higher. The TSS
levels obtained after settling in ponds are adequate for re-
cycling purposes.
8.1.2 Flocculation
Flocculating agents increase the efficiency of set-
tling facilities. They are of two general types: ionic and
polymeric. The ionic types such as alum, ferrous sulfate and
ferric chloride function by neutralizing the repelling double
layer ionic charges around the suspended particles, thereby
allowing the particles to attract each other and agglomerate.
Polymeric types function by physically trapping the particles.
Flocculation agents can be used with minor modifica-
tions and additions to existing treatment systems; but the costs
for the flocculating chemicals are often significant. Ionic
types are used in 10 to 100 mg/£ concentrations in the waste
water while the higher priced polymeric types are effective in
the 2 to 20 mg/£ concentrations.
8.1.3 Clarifiers
Clarifiers, screens and filters are used in less than
1% of the treatment facilities of the mineral mining industry
(EPA, 1976). Clarifiers are essentially tanks with internal
baffles, compartments, sweeps and other directing and segregat-
ing mechanisms to provide efficient concentration and removal
of suspended solids in one effluent stream and clarified liquid
in the other. Screens are restricted to removing the larger
8-2
-------
(50-100 micron) particle size suspended solids which often can
be sold as useful product.
8.1.4 Filtration
Filtration is accomplished by passing the waste water
stream through solids-retaining particulates such as sand,
gravel, coal or diatomaceous earth using gravity, pressure or
vacuum as the driving force. Filtration is versatile in that
it can be used to remove a wide range of suspended particle
sizes. The large volumes of many waste water streams found in
minerals mining operations require large filters. The cost of
these units and their relative complexity, compared to settling
ponds, has restricted their use to a few industry segments com-
mitted to complex waste water treatment.
8.1.5 Water Management Practices
Operational practices at several of the quarries
visited negated the beneficial effects of the treatment processes.
The practice of discharging treated effluent across an unpaved
road that is heavily travelled by trucks causes a resuspension
of particles (Figure 5-14). A culvert under the road to trans-
port the treated effluent to the receiving stream would prevent
the recontamination of the discharge.
Another practice that causes resuspension of solids is
that of allowing the treated discharge to "fall" several feet
from the outfall structure into the stream bed (Figure 5-4).
This practice agitates bottom sediments in the vicinity of the
outfall. Proper design of the outfall structure would prevent
this resuspension of particles.
8-3
-------
In addition, other actions that would reduce impacts
from limestone quarrying on receiving streams include storing
<4 <«o4 -*•% qgnwiAfi -I n rt "f +•*« at-#* 4 *« #« tn a** tti 4 t% ¦? m "t t es a n't t"**" a 1-
auQ vXSXTlg cHHIHmiJlq. XXX. LJL u6 XII u UlZLllU61. LUu u QIXiIll.lIll.u6S IHuXuLc
contamination of streams, and isolating oil storage and oil
wastes from the quarry waste effluent stream.
8.2 Treatment Cost
The effluent control costs for the crushed stone indus-
try are associated with the treatment and storage of suspended
solids. Current treatment practices consist of either direct
discharge, sedimentation ponds or sediment ponds with recycle.
The required ancillary equipment primarily consists of the
water handling system (e.g. pump, pipe, etc.). In some specific
cases a flocculating agent might be necessary to enhance the
settling rate of the suspended solids.
An estimate of costs for a prototype crushed stone
facility was made in 1976 for the EPA Effluent Guidelines
Development Document. This analysis was updated and expanded
in the EPA document "Economic Analysis of Effluent Guidelines,
Mineral Mining and Processing Industry".
Cost information contained in the Development Document
was assembled directly from industry, waste treatment and dis-
posal contractors, engineering firms, equipment suppliers, gov-
ernment sources, and published literature. Whenever possible,
costs were taken from actual installations, engineering estimates
for projected facilities as supplied by contributing companies,
or from waste treatment and disposal contractors quoted prices.
Capital investment estimates for this study were based
on 10 percent cost of capital, representing a composite number
8-4
-------
for interest paid or return on investment required. All cost
estimates were based on August 1972 prices.
The useful service life of treatment and disposal
equipment can vary depending on the nature of the equipment and
process involved, its usage pattern, maintenance care and numer-
ous other factors. Individual companies may apply service lives
based on their actual experience for internal amortization.
The Internal Revenue Service provides guidelines for tax purposes
which are intended to approximate average experience. Based on
discussions with industry and condensed IRS guideline informa-
tion, the following useful service life values were used:
1) General process equipment 10 years
2) Ponds, lined and unlined 20 years
3) Trucks, bulldozers, loaders 5 years
and other such materials
handling and transporting
equipment.
The economic value of treatment and disposal equip-
ment and facilities decreases over its service life. At the
end of the useful life, it is usually assumed that the salvage
or recovery value becomes zero. For IRS tax purposes or inter-
nal depreciation provisions, straight line, or accelerated
write-off schedules may be used. Straight line depreciation
was used solely in the Development Document.
Capital costs were defined as all front-end out-of-
pocket expenditures for providing treatment/disposal facilities.
These costs included costs for research and development neces-
sary to establish the process, land costs when applicable,
equipment, construction and installation, buildings, services,
engineering, special start-up costs and contractor profits and
8-5
-------
contingencies. Most if not all of the capital costs are accrued
during the year or two prior to actual use of the facility.
This present worth sum was converted to equivalent uniform
annual disbursements by utilizing the Capital Recovery Factor
Method:
Pti) (l+i)n
Uniform Annual Disbursement = - £ <—
(l+i)n - i
Where P « present value (capital expenditure),
i = interest rate, X/100,
n * useful life in years
Land-destined solid wastes require removal of land
from other economic use. The amount of land so tied up will
#4 on r\ nn fKo t-Toa / H 4 er»na al ma Arl OTrtTt "I atiH amni in +¦
uc L/ CilLl QII L.L1 Civ L ^ c<3 LIiifcSLI j u x UvJ m d x ulc Lilw vl JL(J V wvl J>U w tlw clHiw vJLl 1 L
of wastes involved. Although land is non-depreciable according
to IRS regulations, there are numerous instances where the mar-
ket value of the land for land-destined wastes has been signi-
ficantly reduced permanently, or actually became unsuitable for
future use due to the nature of the stored waste. The general
criteria applied to costing land are as follows:
1) If land requirements for on-site treatment/dis-
posal are not significant, no cost allowance is
applied.
2) Where on-site land requirements are significant
and the storage or disposal of wastes does not
affect the ultimate market value of the land,
cost estimates include only interest on invested
money.
8-6
-------
3) For significant on-site land requirements where
the ultimate market value and/or availability of
the land has been seriously reduced, cost esti-
mates include both capital depreciation and
interest on invested money,
4) Off-site treatment/disposal land requirements
and costs are not considered directly. It is
assumed that land costs are included in the over-
all contractor's fees along with its other ex-
penses and profit.
5) In view of the extreme variability of land costs,
adjustments have been made for individual industry
situations. In general, isolated, plentiful land
has been costed at $2,470/hectare ($1,000/acre).
Annual costs of operating the treatment/disposal facil-
ities include labor, supervision, materials, maintenance, taxes,
insurance, power and energy. Operating costs combined with
annualized capital costs equal the total costs for treatment
and disposal. No interest cost was included for operating
(working) capital. Since working capital might be assumed to
be one sixth to one third of annual operating costs (excluding
depreciation), about 1-2 percent of total operating costs might
be involved. This is considered to be well within the accuracy
of the estimates.
The Development Document estimated treatment costs
for a single representative facility at four levels of treatment.
In this case, a typical wet crushed stone operation was assumed
to produce 180,000 kkg/yr (200,000 tons/yr), half of which is
washed, and half is dry processed. The assumed wash water
8-7
-------
usage Is 1,000 1/kkg (240 gal/ton), and the assumed waste con-
tent is 6% of the raw material.
Levels of treatment evaluated include:
A - direct discharge
B - settling pond, discharge
C - settling pond, recycle
D - flocculation, settling pond, recycle.
In levels B and C, the waste water is passed through
a one acre settling pond and discharged or recycled back to the
facility. The pond is dredged periodically and the sludge is
deposited on site.
Level D involves settling with flocculents and recycle.
The waste water is treated with a flocculent and passed through
a one acre settling pond. The effluent is then recycled. How-
oifof i f i c rjiTft t-Kflf- o f 1 out* t\rrn 11 H Ko f-rs nrAflfi^o
US' it G* >«» p w* aB*»k C3L JLi 1* »l» L CX Q* «Lk> JL» Vm* Km* JL» d* m V-# JL» \Jt *5* £> JLCm Vp* ^ Vp*
an effluent quality acceptable for recycle in a crushed stone
operation.
8-8
-------
Unit costs used in this analysis were as follows;
Level B
Pond Cost $10,000
Pumps and piping 4,500
Power 1,000
Pond cleaning 6,000
Taxes and insurance 400
Level C
Total pond cost $10,000
Total pump and piping cost 9,000
Annual capital recovery 3,100
Power 2,000
Pond cleaning 6,000
Taxes and insurance 400
Level D
Additional capital flocculent $ 3,500
equipment
Additional annual capital 600
Annual chemical cost 1,000
It should be noted here that the value for power associated
with pumping can vary widely depending on the topography of the
site. In areas of high relief, the cost of pumping for recycle
may be prohibitive.
The Development Document estimated capital cost, oper-
jst'inO1 an A m *3 *i fi an 3t*i no ^Aefc an e\ «Aet*e TTi ao a t.taya -»•% -y
dLlug dilvJ. tllalUwcuautc tUo lo dllu. cucl gy tUaLb , iilcoc WcCc pre"
sented separately as total annual cost and as cost/kkg of
product. A subsequent study updated the values in the Document
to mid-1974 dollars and expanded the analysis to include three
additional plant sizes: 91,000 metric tons/year, 1,270,000
metric tons/year and 2,180,000 metric tons/year. The costs
shown in the Development Document were modified in the Economic
Analysis of Effluent Guidelines by using a GNP inflator of 16.5%
(Reference EPA, 1977). Fixed capital costs were varied by the
8-9
-------
ratios of annual production costs raised to the 0.9 power,
based on the 182,000 metric tons/year model plant size in the
Development Document. Operating costs were varied as a direct
function of plant capacity.
Tables 8-1 through 8-4 present the treatment costs for
the four plant sizes. These costs were updated to 1978 dollars
using a GNP deflator from 1974 to 1978 of 1.308.
As the tables indicate, treatment costs per ton of
product vary only slightly with plant capacity. Allowing dis-
charge from sedimentation ponds as opposed to requiring recycle
would save the operator $0,028/ton wet process while causing no
significant increase in suspended solids load. During the time
EPA regulations requiring recycle were promulgated, no quarries
were known to have closed due to prohibitive wastewater treat-
ment costs. However, in many instances, costs for treatment
were much higher than EPA estimates (NCSA, 1980). The average
cost for treatment with a settling pond only is $0.167/ton wet
process. If flocculation is required, costs will increase ap-
proximately $0.026/ton wet process. The majority of this cost
is expected to be passed on to the consumer.
8-10
-------
TABLE 8-1.
Plant Size;
Plant Age:
Base Year;
PROCESS WATER COMPLIANCE COST FOR MODEL WET PROCESS
Crushed Stone Facility
Metric Tons Per Year of Product
Plant Location: Rural Location
Near Population Center
Level
91,000 Total
(45,500 Wet)
40 Years
1978
B
Invested Capital Costs:
Total
Annual Capital Recovery
Operating and Maintenance
Costs:
Annual 0 & M (excluding
power and energy)
Annual energy and power
Total Annual Costs
Cost/Metric Ton/Wet Process
D
0
11,910
15,700
18,580
0
1,830
2,360
2,880
0
4,970
4,970
5,630
0
780
1,570
1,570
0
7,580
8,900
10,080
0
0.167
0.196
0.222
Level Description:
A - direct discharge
B - settling pond, discharge
C - settling pond, recycle
D - flocculent, settling pond, recycle
8-11
-------
TABLE
Plant Size
Plant Age:
Base Year:
8-2. PROCESS WATER COMPLIANCE COST FOR MODEL WET PROCESS
Crushed Stone Facility
180,000 Total Metric Tons Per Year of Product
Plant Location: Rural Location
Near Population Center
Level
(90,000 Wet)
40 Years
1978
B
Invested Capital Costs:
Total
Annual Capital Recovery
A f»> qt* at* i ti rr qti n M a i t"i ~* qti a t"i /"* a
|p w X» a L> JL11^ Hi I vi L ia IlL- w I id 1 iv t
Costs :
Annual 0 & M (excluding
power and energy)
Annual energy and power
Total Annual Costs
Cost/Metric Ton/Wet Process
D
0
22,110
28,920
34,280
0
3,660
4,710
5,630
0
9,810
9,810
11,250
0
1,570
3,010
3,010
0
15,050
17,530
19,890
0
0.167
0.194
0.220
Level Description:
A - direct discharge
B - settling pond, discharge
C - settling pond, recycle
D - flocculent, settling pond, recycle
8-12
-------
TABLE 8-3.
Plant Size:
Plant Age:
Base Year:
PROCESS WATER COMPLIANCE COST FOR MODEL WET PROCESS
Crushed Stone Facility
1,270,000 Total Metric Tons Per Year of Product
Plant Location: Rural Location
Near Population Center
Level
(635,000 Wet)
40 Years
1978
B
D
Invested Capital Costs:
Total
Annual Capital Recovery
Operating and Maintenance
Costs :
Annual 0 & M (excluding
power and energy)
Annual energy and power
Total Annual Costs
Cost/Metric Ton/Wet Process
0
128,230
167,880
198,890
0
25,910
1 33,240
39,650
0
69,220
69,220
79,430
0
11,120
21,200
21,200
0
106,250
123,660
140,280
0
0.167
0.195
0.221
Level Description:
A - direct discharge
B - settling pond, discharge
C - settling pond, recycle
D - flocculent, settling pond, recycle
8-13
-------
TABLE 8-4. PROCESS WATER COMPLIANCE COST FOR MODEL WET PROCESS
Crushed Stone Facility
Metric Tons Per Year of Product
Plant Location: Rural Location
Near Population Center
Level
Plant Size: 2,130,000 Total
(1,076,000 Wet)
Plant Age:
Base Year;
40 Years
1978
B
Invested Capital Costs:
Total
Annual Capital Recovery
Operating and Maintenance
Costs:
Annual 0 & M (excluding
power and energy)
Annual energy and power
Total Annual Costs
Cost/Metric Ton/Wet Process
D
0
208,710
272,950
323,592
0
34,540
44,489
53,125
0
118,810
118,810
136,350
0
18,970
36,510
36,510
0
172,320
199,810
225,980
0
0.161
0.187
0.212
Level Description:
A - direct discharge
B - settling pond, discharge
C - settling pond, recycle
B - flocculent, settling pond, recycle
8-14
-------
9.0 REFERENCES
1. American Public Health Association, American Water Works
Association, and Water Pollution Control Federation, Standard
Methods for the Examination of Water and Wastewater, Fourteenth
Edition, 1976.
2. Bachmann, R. W., The Ecology of Four North Idaho Trout
Streams with Reference to the Influence of Forest Road Construc-
tion. M.S. Thesis University of Idaho, 97 pp (unpublished) 1958.
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•tr.S. GQTHtlMHK PRIMING OFFICE I 1982 0-561-OB5/4457
9-12
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9
TECHNICAL REPORT DATA
(Please read Instructions on the reverse before completing)
t. REPORT NO. 2.
EPA 440/1-82/059
3, RECIPIENT'S ACCESSION NO.
PB82 2 4 220 7
4. TITLE AND SUBTITLE
The Effects of Discharges from Limestone Quarries on
Water Quality and Aquatic Biota
5. REPORT DATE
June 15, 1982
6. PERFORMING ORGANIZATION CODE
7 AUTHQR(S)
M. A. Hoban Ronald Kirby N.A. Pacharzina
J.C. Lippe M.H. McCloskey
8. PERFORMING ORGANIZATION REPORT NO.
9. PERFORMING ORGANIZATION NAME AND ADDRESS !
U. S. Environmental Protection Agency
Office of Water, Effluent Guidelines Division
401 M. Street S.W.
Washington, D.C. 20460
10. PROGRAM ELEMENT NO.
11. CONTRACT/GRANT NO.
12. SPONSORING AGENCY NAME AND ADDRESS
U.S. Environmental Protection Agency
Office of Water, Effluent Guidelines Division
401 M. Street S.W.
Washington, D.C. 20460
13. TYPE OF REPORT AND PERIOD COVERED
Final
14. SPONSORING AGENCY CODE
15, SUPPLEMENTARY NOTES
16. ABSTRACT
This report documents the procedures, wastewater analysis results, water quality
effects and biological effects of limestone quarring and processing operations on
surface streams. Data was gathered by on site sampling of process steams (treated
and untreated) at nine limestone operations and biological sampling of the receiving
streams. Published data was gathered on the genral effects of constitutents present
in wastewater streams and effects of limestone effuents are evaluated on information
from the literature and sampling.
17. KEY WORDS AND DOCUMENT ANALYSIS
a. DESCRIPTORS
b. IDENTIFIERS/OPEN ENDED TERMS
C. COSATI Field/Group
environmental effects
wastewater analysis
quarry wastewater discharges
limestone quarries
wastewater treatment
18. DISTRIBUTION STATEMENT
Release to Public
19. SECURITY CLASS (ThisReportf
unclassified
21. NO. OF PAGES
175
20. SECURITY CLASS (This page)
unclassified
22. PRICE
EPA Form 2220-1 (9-73! '
t
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