Hydrogeology and Water Quality at the 

St. Francois County Landfill and VicinitySoutheastern Missouri, 1990-94

By J.G. SCHUMACHER and E.A. HOCKANSON

U.S. GEOLOGICAL SURVEY 

Water-Resources Investigations Report 96-4022

Prepared in cooperation with the

ST. FRANCOIS COUNTY ENVIRONMENTAL CORPORATION

Rolla, Missouri 

1996
U.S. DEPARTMENT OF THE INTERIOR 

BRUCE BABBITT, Secretary

U.S. GEOLOGICAL SURVEY 

Gordon P. Eaton, Director

For additional information Copies of this report may be

write to: purchased from:

District Chief U.S. Geological Survey

U.S. Geological Survey Information Services

1400 Independence Road Box 25286

Mail Stop 100 Denver Federal Center

Rolla, Missouri 65401 Denver, Colorado 80225
CONTENTS

Abstract..................................................................................................^ 1

Introduction...........................................................................................................................................^ 2

Purpose and Scope.................................................................................................................................................... 2

Description of the Study Area.................................................................................................................................. 2

History of the Study Area......................................................................................................................................... 4

Previous Investigations............................................................................................................................................. 9

Acknowledgments.................................................................................................................................................... 11

Methods of Investigation.................................................................................................................................................... 11

Information Search and Well Inventory................................................................................................................... 12

Monitoring Well and Piezometer Installation........................................................................................................... 12

Water and Soil Sampling Methods........................................................................................................................... 13

General Characteristics of Municipal Solid Waste and Leachate Production.................................................................... 16

Waste Composition.............................................................^ 20

Waste Degradation and Leachate Production........................................................................................................... 20

Surface- Water Hydrology................................................................................................................................................... 22

Hydrogeology..................................................................................................................................................................... 22

Geology.................................................................................................................................................................... 23

Regional Hydrogeology............................................................................................................................................ 25

Hydrogeology of the St. Francois County Landfill Site........................................................................................... 34

Water Quality...................................................^ 40

Regional Ground-Water Quality............................................................................................................................... 42

Background Ground-Water Quality at the Landfill Site and Vicinity...................................................................... 42

Physical Properties and Inorganic Constituents............................................................................................. 43

Pesticides and Volatile Organic Compounds.................................................................................................. 49

Distribution of Contaminants in Ground Water........................................................................................................ 50

Physical Properties and Major Inorganic Constituents................................................................................... 51

Trace Elements ............................................................................................................................................... 53

Pesticides and Volatile Organic Compounds.................................................................................................. 54

Surface-Water Quality.............................................................................................................................................. 57

Effects of the Landfill on Water Quality............................................................................................................................. 57

Tailings......................................................................................._ 62

Bedrock and Mines................................................................................................................................................... 63

Surface Water............................................................................................................................................................ 64

Summary and Conclusions................................................................................................................^ 65

References Cited................................................................................................................................................................. 67

Contents III
FIGURES 

1-3. Maps showing:

1. Location of the St. Francois County Landfill site....................................................................................... 3

2. Location of major features and topography of the Desloge tailings pile, including the St. Francois

County Landfill site, Missouri..................................................................................................................... 5

3. Current (1994) features at the St. Francois County Landfill site, Missouri................................................ 6

4. Photograph showing typical underground workings in the Old Lead Belt, southeastern Missouri.................... 7

5. Map showing sampling sites at the St. Francois County Landfill site, Missouri................................................. 10

6. Graphs showing phases of solid waste degradation and leachate production..................................................... 21

7. Map showing regional geology in the vicinity of the St. Francois County Landfill site, Missouri..................... 24

8. Generalized stratigraphic column for the Old Lead Belt area, southeastern Missouri........................................ 26

9. Map showing pre-1972 potentiometric surface of the St. Francois aquifer in the vicinity of the St.

Francois County Landfill site, Missouri.............................................................................................................. 28

10. Map showing potentiometric surface of the lower part of the St. Francois aquifer (1992-93) in the

vicinity of the St. Francois County Landfill site, Missouri.................................................................................. 32

11. Graph showing seasonal variation of mine water levels in the vicinity of the St. Francois County

Landfill site, Missouri.......................................................................................................................................... 33

12. Map showing potentiometric surface in the tailings and shallow bedrock at the St. Francois County

Landfill site, Missouri, in November 1993.......................................................................................................... 37

13. Map showing altitude of original land surface beneath the St. Francois County Landfill site, Missouri............ 38

14. Hydrogeologic sections at the St. Francois County Landfill site, Missouri........................................................ 39

15. Map showing extent of underground mine workings and location of abandoned exploration drill holes

beneath the St. Francois County Landfill site, Missouri...................................................................................... 41

16. Trilinear diagram of major constituents in ground-water samples from the St. Francois County Landfill

site and vicinity, Missouri.................................................................................................................................... 47

17-21. Graphs showing:

17. Total mass of pesticides and volatile organic compounds detected in ground-water samples

collected in October 1993, St. Francois County Landfill site, Missouri..................................................... 55

18. Example of results from analysis of variance and multiple-comparison tests............................................ 58

19. Results of analysis of variance and multiple-comparison tests on ranked data for selected physical 

properties and chemical constituents from tailings monitoring wells and piezometers at the 

St. Francois County Landfill site, Missouri................................................................................................. 59

20. Results of analysis of variance and multiple-comparison tests on ranked data for selected physical 

properties and chemical constituents from bedrock piezometers at the St. Francois County 

Landfill site, Missouri................................................................................................................................. 60

21. Results of analysis of variance and multiple-comparison tests on ranked data for selected physical 

properties and chemical constituents from wells completed in mine cavities in the vicinity of the 

St. Francois County Landfill site, Missouri................................................................................................. 61

IV Contents
TABLES

1. Completion data for landfill wells and piezometers, St. Francois County Landfill site, Missouri...................... 14

2. Detection levels and drinking water regulatory limits for organic compounds................................................... 17

3. Typical physical composition of municipal solid waste and moisture content of waste components................. 20

4. Common constituents of landfill leachate............................................................................................................ 23

5. Well inventory data for selected domestic and public-supply wells in the vicinity of the St. Francois

County Landfill site, Missouri............................................................................................................................. 29

6. Grain size, bulk mineralogy, and selected chemical composition of tailings and overburden samples,

St. Francois County Landfill site, Missouri......................................................................................................... 35

7. Range of selected physical properties and chemical constituents in samples from selected public-supply

wells completed in the St. Francois aquifer, Missouri......................................................................................... 43

8. Range of selected physical properties and chemical constituents from background sites in the tailings,

shallow bedrock, and mine cavities in the vicinity of the St. Francois County Landfill site, Missouri.............. 44

9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers

in the vicinity of the St. Francois County Landfill site, Missouri........................................................................ 73

10. Molar ratios of calcium to magnesium and saturation indices for selected mineral phases in water

samples from background sites in the vicinity of the St. Francois County Landfill site, Missouri..................... 48

11. Concentrations of pesticides detected in water samples from monitoring and public-supply wells in the

vicinity of the St. Francois County Landfill site, Missouri.................................................................................. 49

12. Concentrations of volatile organic compounds detected in water samples from monitoring and publicsupply wells, piezometers, seeps, surface-water sites, and quality assurance/quality control 

samples in the vicinity of the St. Francois County Landfill site, Missouri.......................................................... 114

13. Physical properties and concentrations of inorganic constituents in samples from seeps and surface

water in the vicinity of the St. Francois County Landfill site, Missouri.............................................................. 120

Contents
Hydrogeology and Water Quality at the St. Francois 

County Landfill and Vicinity, Southeastern Missouri 

1990-94

ByJ.G. Schumacher anc/E.A. Hockanson 

Abstract

An investigation of the hydrogeology and 

water quality at the St. Francois County Landfill 

was conducted because of concern about possible 

ground-water contamination. The 53-acre landfill 

is located in the southern part of an abandoned 

lead-mine tailings pile and was operated from 

1973 to 1993. The tailings pile is one of several 

that are the remains of more than a century of lead 

mining in the Old Lead Belt of southeastern Missouri. The bedrock directly beneath the tailings 

pile consists of massively bedded dolostone of the 

Bonneterre Formation. The formation at the site is 

about 300 feet thick, and the lower 100 feet were 

mined extensively. The Bonneterre Formation and 

underlying Lamotte Sandstone comprise the St. 

Francois aquifer, which is used extensively in the 

region for domestic and public-water supply. The 

abandoned water-filled mine cavities are used 

locally for domestic and public-water supply.

The landfill is located in an area where the 

tailings filled a small creek valley that contained a 

tributary to the Big River. The buried creek valley 

slopes toward the Big River to the northeast 

where the tailings are more than 100 feet thick. 

Within the buried valley near the middle of the 

site, a portion of the tailings is saturated to a 

thickness of more than 50 feet, and the water table 

is within 15 feet of buried refuse. A ground-water 

mound extends east-west across most of the landfill site the nose of which coincides with the 

middle part of the buried creek valley. In this area 

a downward vertical gradient exists between the

tailings, the underlying Bonneterre Formation, 

and the abandoned mine cavities about 200 feet 

below the tailings surface.

The landfill has affected the ground-water 

quality in the tailings and shallow bedrock at the 

site. Landfill leachate has migrated into these 

media as evidenced by increased specific conductance values and increased concentrations of calcium, sodium, total alkalinity, chloride, total 

ammonia, barium, iron, pesticides (diazinon and 

terbacil), and volatile organic compounds (for 

example, dichloromethane, chlorofluoromethane, 

dichlorofluoromethane, chloroethane, 1,1-dichloroethane, vinyl chloride, cis-l,2-dichloroethene, 

trans-l,2,-dichloroethene, and ethyl ether). In 

general, the effects of the landfill were greatest in 

the tailings and Big River alluvium northeast of 

the landfill. With the exception of this area, the 

available data indicate that contaminants from the 

landfill have not migrated offsite. Although samples from several bedrock piezometers contained 

large concentrations of inorganic constituents 

indicative of landfill leachate, only small (less 

than 4 nanograms per liter) concentrations of 

diazinon attributable to the landfill were detected 

in those samples.

Small concentrations of two pesticides 

(diazinon and prometon) and volatile organic 

compounds (1,1,1-trichloroethane, 1,1-dichloroethene, cis-1,2-dichloroethene, 1,1,2-trichloroethene, 1,1,2,2-tetrachloroethene, and methyltertiarybutylether) were detected in the abandoned mine cavities beneath the landfill. Prometon, 1,1,2-trichloroethene, 1,1,2,2-tetraAbstract
chloroethene, and methyltertiarybutylether, however, were detected in samples from background 

mine sites several miles from the landfill, indicating other sources of contamination in the mines 

unrelated to the landfill.

INTRODUCTION

The State of Missouri enacted legislation in 

1972 governing the disposal of municipal solid waste 

because of concerns regarding the effect of municipal 

solid waste landfills on ground-water quality. Legislation governing permitting and ground-water monitoring at municipal solid waste landfills (MSWLF) was 

promulgated in 1976 and revised in 1988. These rules 

require installation of ground-water monitoring networks at facilities of particular concern to the Missouri 

Department of Natural Resources (Missouri DNR) and 

at all facilities applying for expansion permits. The 

goal of this legislation is to protect ground-water supplies by gaining information relating to site geology, 

source and direction of ground-water flow, and 

ground-water quality. In 1991, the U.S. Environmental 

Protection Agency (USEPA) enacted legislation containing stringent design and monitoring requirements 

on all MSWLF hi the United States. Most provisions 

under legislation were delayed until October 9, 1993, 

when all MSWLF became regulated under 40 CFR 

part 258 (Code of Federal Regulations, 1992).

Ground water supplies all of the drinking water 

in St. Francois County. In 1990 the U.S. Geological 

Survey (USGS), in cooperation with the St. Francois 

County Environmental Corporation, began a hydrologic and water-quality investigation at the St. Francois County Landfill and vicinity to determine the 

water quality in the vicinity of the landfill and the 

effects of the landfill on ground- and surface-water 

quality in the area.

Purpose and Scope

This report presents the results of a hydrogeologic investigation at the St. Francois County Landfill 

from 1990 to 1994. This report describes: (1) the 

methods of investigation used in this study; (2) the 

general characteristics of municipal solid waste and 

leachate production; (3) the regional hydrogeology 

and water quality of the St. Francois aquifer in the 

vicinity of the St. Francois County Landfill; (4) the

hydrogeology and water quality of the St. Francois 

County Landfill site; and (5) the effects of the landfill 

on ground- and surface-water quality, including the 

distribution of landfill contaminants in ground water.

From 1990 to 1994 more than 100 water-quality 

samples were collected from 32 ground-water and 5 

surface-water sites by the USGS. Analytical results of 

water-quality samples collected during previous investigations in the area by the USGS (Smith and Schumacher, 1991), the St. Francois County Landfill, the 

Missouri DNR, and the USEPA also were used in this 

investigation. The geochemical controls on trace-element mobility were evaluated through laboratory 

leaching studies performed at the Department of Geology, Kansas State University. The laboratory studies 

included more than 25 individual experiments interacting landfill leachate with mine tailings from the 

site. Interpretation of ground-water geochemistry was 

aided by the use of statistical and graphical techniques 

and by the geochemical code WATEQ4F (Ball and 

others, 1987).

Description of the Study Area

The St. Francois County Landfill is located 

about 70 mi (miles) south of St. Louis (fig. 1) and 

about 0.5 mi west of the city of Desloge in St. Francois 

County, Missouri. The landfill, closed on October 6, 

1993, is one of two landfills in Missouri where municipal solid wastes have been placed within an abandoned lead mine tailings pile. The 600-acre tailings 

pile, known locally as the Desloge tailings pile, is one 

of six large tailings piles that are the remains of more 

than a century of lead mining in the Old Lead Belt of 

southeastern Missouri. The landfill site is located 

within the Salem Plateau of the Ozark Plateaus physiographic province (Fenneman, 1938). Topography in 

the area is rugged with narrow, steep drainages and 

several hundred feet of relief. Mean annual precipitation in the area is about 40 in. (inches; National Oceanic and Atmospheric Administration, 1988); 

however, seasonal thunderstorms can produce intense 

precipitation. For example, a series of severe thunderstorms at the landfill site on September 22 and 23, 

1993, deposited 7.5 in. of rainfall in 18 hours.

Most of the Desloge tailings pile is located 

within a meander loop of the Big River, a perennial 

stream with an annual mean discharge of 190 ft3/s 

(cubic feet per second; Reed and others, 1995) at Irondale, about 15 mi upstream of the tailings pile. The

2 Hydrogeology and Water Quality at the St. Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
90-3T30" 

38'

30'

37'5230m

37'45'

EXPLANATION

MINED AREA OF THE OLD LEAD BELT 

TAILINGS PILE

2 MILES

0 1 2 KILOMETERS

Rgure 1. Location of the St. Francois County Landfill site.

Introduction 3
tailings pile borders the Big River for more than 3 mi 

along this meander loop. The tailings were deposited 

on either side of a north-trending ridge located in the 

middle of the meander loop (fig. 2). Much of the ridge 

was not covered by tailings and consists of hardwood 

forest with scattered pine trees. The northeast corner 

of the permitted sanitary landfill is within 500 ft (feet) 

of the Big River along the east side of the meander 

loop (fig. 3). Hereinafter, the term landfill site refers to 

approximately a 100-acre tract in the southern part of 

the Desloge tailings pile containing the former 43-acre 

sanitary landfill, former 10-acre demolition fill, landfill office-machine shop, scale house, and recently 

(1994) constructed transfer and recycling stations (fig. 

3). The term landfill refers to the 53-acre tract used for 

the disposal of municipal solid waste (sanitary landfill) 

and demolition wastes (demolition fill). The location 

and size of the sanitary landfill (43 acres) and demolition fill (10 acres) vary from the tracts originally permitted by the Missouri DNR for the disposal of 

sanitary refuse (permitted sanitary landfill) and demolition wastes (permitted demolition fill) as shown in 

figure 3.

The Desloge tailings pile can be separated into 

three general regions: the large 100-acre chat pile to 

the east and the middle and lower tailings piles (about 

504 acres) in the south-central and northern areas of 

the site (fig. 2). The chat pile, consisting of medium to 

coarse sand-size particles, rises more than 200 ft 

above the Big River and is one of the highest topographic features in the area. Tailings comprising the 

middle and lower piles generally are fine silt- and 

clay-size particles with some fine to medium sand-size 

particles. These areas are referred to locally as "slime" 

ponds because of their soupy consistency when wet. 

The middle tailings pile, containing the landfill, consists of tailings generally east of the north-trending 

ridge. The nearly flat surface of this pile extends about 

100 to 110 ft above the Big River. Tailings west and 

north of the ridge comprise the lower pile that extends 

about 30 to 40 ft above the Big River. Excluding the 

landfill, the tailings generally are devoid of vegetation 

except for scattered small trees where the tailings are 

less than a few feet thick or along the toe of slopes.

The middle and lower tailings piles, including 

the landfill, are currently owned by the St. Francois 

County Environmental Corporation. The chat pile and 

several acres south of the landfill are owned by the St. 

Joseph Minerals Corporation. About 12 acres immediately west of the landfill site between the tailings pile

and Big River are owned by St. Francois County. The 

remaining land southwest, north, and east of the tailings pile is privately owned. Subdivisions of the city 

of Desloge are less than 0.5 mi east of the landfill site. 

Several private homes along the access road immediately southwest of the landfill obtain drinking water 

from domestic wells, several of which are within 500 

ft of the landfill site. The nearest public-supply well is 

located in the city of Desloge about 1 mi east of the 

landfill site.

History of the Study Area

The discovery of vast deposits of disseminated 

lead ore in the Old Lead Belt was facilitated by the 

introduction of the diamond core drill by the St. 

Joseph Lead Company in 1869 (Snyder and Gerdemann, 1968). Exploration increased rapidly, and as 

many as 15 companies operated in the region in the 

late 1800's. Mining operations ceased in the Old Lead 

Belt in 1972 with depletion of the ore body and discovery of richer ore about 40 mi southwest near Viburnum, Missouri. Presently (1994) about 8 mi2 (square 

miles) are underlain by abandoned, water-filled mine 

cavities (shown in fig. 1 as mined area).

Subsurface mining operations were conducted 

at and in the vicinity of the landfill site from 1893 to 

1958 when the ore body was depleted (St. Joseph Minerals Corporation, 1993). The 286-ft deep Desloge No. 

3 mine shaft was located about 300 ft east of the southeast corner of the landfill property (fig. 2). Most of the 

mining was conducted using a room and pillar method 

with a network of interconnecting slopes. Many rooms 

were large enough to contain working faces of 50 ft or 

more (fig. 4). Early milling operations used a gravity 

method to separate ore minerals from the dolomitic 

host rock. Waste from this process, called chat, consisting of medium to coarse sand-size particles, was 

placed in large piles with heights in excess of 100 ft by 

conveyors. This is the origin of the chat pile immediately east of the landfill. In 1910 the flotation separation process was introduced. This process involved 

grinding the ore much finer and the use of chemical 

reagents, such as sodium cyanide (NaCN), creosote, 

and xanthate (short-chain aliphatic organic compounds containing two sulfur atoms), to extract fine 

particles of galena. Waste from the flotation process 

was called tailings. The tailings were finer than chat 

and ranged from fine silt- and clay- to medium sandsize particles. A series of dams comprised of chat and

4 Hydrogeology and Water Quality at the St. Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
90'33'30" 33'10" 32'50"

37'53'35"

53'15"

52'55"

52'35"

90'32'30" 

I

EXPLANATION

0 300 600 900 FEET

I i h 

0 100 200 300 METERS

HI TAILINGS DESLOGE CITY LIMIT 

 750 TOPOGRAPHIC CONTOUR Interval 10 feet. Datum is sea level GROUND- OR SURFACE-WATER SAMPLING SITE

 RESIDENCE 

H DESLOGE NO. 3 MINE SHAFT

ST. FRANCOIS COUNTY ENVIRONMENTAL 

CORPORATION PROPERTY LINE

LANDFILL

Rgure 2. Location of major features and topography of the Desloge tailings pile, including the St. Francois 

County Landfill site, Missouri.

Introduction 5
90'33' 32f50" 32'40"

37'52'45"

52'35"

37'52'25"

90'32'30"

I

PERMITTED

SANITARY

LANDFILL

Diversion 

tunnel Tailings 

dam

Landfill officemachine shop

\

I \

300 600 900 FEET

100 200

\ 

300 METERS

EXPLANATION

IH APPROXIMATE AREA OF THE 

OLD DESLOGE CITY DUMP

El ST. FRANCOIS COUNTY LANDFILL

----- ST. FRANCOIS COUNTY ENVIRONMENTAL 

CORPORATION PROPERTY LINE

--- ROAD

Figure 3. Current (1994) features at the St. Francois County Landfill site, Missouri.

6 Hydrogeology and Water Quality at the St. Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
00

o

O)

o

=] m

E

e

0) 

CD

o

0)

to

D)

C

'£o

O)

E

Introduction
coarser tailings was constructed across the Mine-AJoe Creek valley immediately west of the chat pile and 

mill complex to contain the tailings. The creek valley 

was filled, and a diversion tunnel was cut through the 

north trending ridge to divert Mine-A-Joe Creek 

around the tailings pond (fig. 2). Part of the filled 

Mine-A-Joe Creek valley is now overlain by the St. 

Francois County Landfill.

Between closing of the mine and mill at Desloge 

in 1958 and the early 1970's, about 5 acres along the 

southwest corner of the Desloge tailings pile were 

used as a dump by the city of Desloge (T.O. Seiberling 

Engineering and Surveying Company, Bonne Terre, 

Missouri, written commun., 1974). The location of 

this dump is uncertain; however, during a site reconnaissance in 1989, trash and debris were observed several hundred feet northwest of the landfill office in 

what is shown in figure 3 as the old Desloge City 

Dump.

The St. Francois County Landfill began operation on July 2,1973. The landfill was designed as a 

moving trench landfill in which sanitary refuse was to 

be placed in a series of shallow trenches. Initial design 

specifications called for a series of north-south trending trenches 100 ft long, approximately 25 ft wide, and 

8 to 10 ft deep to be constructed along the eastern edge 

of the permitted sanitary landfill. The refuse was to be 

placed in alternating "lifts" no more than 2 ft thick and 

covered daily with 6 in. of fine tailings. Refuse placement occurred in two general phases phase I and 

phase n.

During phase I (1973 to about 1983) refuse was 

placed in excavations along the eastern one-third of 

the permitted sanitary landfill area, and a demolition 

fill was operated (sometime between about 1974 and 

1983) along the western boundary of the permitted 

demolition fill area (fig. 3). The first refuse trench was 

constructed in the southeast corner of the site and the 

trench was filled in a south to north manner. Refuse in 

this area was placed at depths less than 15 ft. Shortly 

after the landfill opened, however, the original trench 

design was modified, trenches were excavated as wide 

and deep as possible, and the landfill was operated 

essentially as an area fill. Refuse was placed to and 

possibly across the east property line near the chat pile 

(fig. 3). Several areas along this boundary were excavated to bedrock, which was encountered at relatively 

shallow depths (less than 20 ft) in some places. The 

shallow excavations in this area were overfilled, and 

refuse was piled into a large mound and left exposed

for some time. During the late 1970's and early 

1980's, refuse was placed into a large excavation more 

than 40 ft deep in the northeast corner of the site. This 

area was also left exposed for some time.

Phase II began about 1983 when a large central 

trench 20 to 30 ft deep, more than 300 ft wide, and 

extending the entire length of the permitted area, was 

excavated in the middle part of the permitted sanitary 

landfill. Material removed during the excavation of 

this trench was placed over exposed refuse in the 

northeast corner of the permitted area and stockpiled 

on top of the demolition fill. The altitude of the trench 

floor was about 760 ft with a gradual slope to the south 

where runoff entered Mine-A-Joe Creek through a 

breach in the south tailings dam adjacent to the drainage tower (fig. 3). The western part of the original 

phase I fill that was placed at shallow depths was 

removed and placed in the phase II trench. Refuse disposal began in the northern end of the phase n trench 

and progressed southward until about one-half the 

trench was filled before the landfill ceased operation. 

The western slope of this fill extended over the northern part of the demolition fill. Between 20 and 40 ft of 

refuse was placed in the northern one-half of the 

trench. Unlike phase I, however, the refuse was placed 

in lifts and compacted, daily covers were applied, and 

attempts at controlling runoff were implemented gradually.

In the late 1970's, brush and thousands of tires 

were dumped into two large gullies several hundred 

yards north of the permitted area. Since the late 

1980's, brush has been placed along the slopes and 

across the top of the northern end of the middle tailIngs pile in an attempt to control erosion. Beginning in 

about 1988, appliances and scrap metal were separated 

and stockpiled north of the landfill office for recycling 

(fig. 3). In addition, the breach through the south tailings dam (fig. 2) was closed and replaced by a culvert 

and a new drainage structure in an attempt to control 

the release of tailings into Mine-A-Joe Creek. The 

south end of the phase II trench was excavated down 

to bedrock (approximately an altitude of 730 ft) to 

serve as a holding basin where runoff was temporarily 

contained to allow suspended solids to settle.

The landfill closed on October 6,1993, leaving 

St. Francois County without a solid waste disposal 

facility. Work began on a transfer station and recycling 

center at the landfill site in November 1993. A permit 

for operation of a transfer station was issued on

8 Hydrogeology and Water Quality at the St. Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
December 22,1993, and operations began in January 

1994.

Previous Investigations

The final engineering report on the St. Francois 

County Landfill was issued in June 1974 (T.O. Seiberling Engineering and Surveying Company, written 

commun., 1974). This report indicated several perched 

water tables were encountered while excavating 

trenches at the site, and as a result, trench size and 

depth varied according to the stability of the tailings. 

At this time the tailings were thought to be relatively 

impermeable, and contamination of drinking water 

supplies by the landfill was believed unlikely.

Gastreich (1974) concluded that the St. Francois 

County Landfill had a low probability of affecting 

ground- and surface-water quality in the area, but suggested a ground-water monitoring network be installed 

and measures taken to control rainfall infiltration into 

exposed refuse in the trenches. Based on analytical 

results from water-quality samples collected in 1974, 

Gastreich concluded none of the water samples were 

affected by the landfill at that time, but suggested 

leachate generated in the landfill probably would 

migrate down the buried Mine-A-Joe Creek valley 

beneath the landfill toward the Big River. During trips 

to the site, Gastreich noticed several trenches had 

encountered perched water tables. Laboratory permeability tests (Gastreich, 1974) determined that the permeability of the tailings ranged from 2.5 x 10~9 ft/s 

(feet per second) for the fine silt-size particles to 2.5 x 

10~7 ft/s for the fine sand-size particles. The permeability of the chat and coarse sand-size particles comprising the tailings dams was 2.5 x 10"4 ft/s.

In their assessment of measures to control the 

discharge of tailings into the Big River after a large 

release in 1977, Novack and Hasselwander (1980) 

expressed serious concerns about landfill leachate, 

potentially with a low pH value and a high organic 

content, leaching large quantities of trace elements 

such as lead (Pb) and zinc (Zn) from the tailings and 

transporting these as organo-metallic complexes to the 

Big River. The report recommended that the Missouri 

DNR begin an immediate monitoring study of the 

landfill to locate and characterize any leachate 

observed.

In response to the Novack and Hasselwander 

(1980) study, the Missouri DNR, Division of Environmental Quality (Missouri DEQ) and Missouri DNR,

Division of Geology and Land Survey (Missouri 

DGLS) conducted a joint water-quality reconnaissance of the landfill site (Tom Ellis, Missouri Department of Natural Resources, Solid Waste Management 

Program, written commun., 1980; J.H. Williams, Missouri Department of Natural Resources, Division of 

Geology and Land Survey, written commun., 1980). A 

total of eight water-quality samples was collected 

from the Big River, Mine-A-Joe Creek, a seep southwest of the landfill, and a flowing drill hole about 

1,000 ft west of the site. A seep southwest of the landfill (seep G, fig. 5) emerges from a concrete tunnel 

connected to the original drainage tower east of the 

landfill office. Before about 1988, the tunnel was connected to the drainage tower by an 8-in. diameter iron 

pipe. Based on the analytical results, the Missouri 

DEQ and Missouri DGLS concluded that the landfill 

was not contaminating the Big River or Mine-A-Joe 

Creek, but the large total lead (Pbt) concentration, 106 

|ig/L (micrograms per liter), in a sample from a flowing drill hole west of the landfill site (fig. 5) was a concern because this drill hole is completed in the flooded 

mine cavities that are used as a drinking-water source 

in the area.

Hydro-Search, Inc. evaluated the potential for 

regional ground-water contamination from the Desloge tailings pile and the St. Francois County Landfill 

in 1986 (Craig Eison, Hydro-Search, Inc., written 

commun., 1986). They noted several flowing drill 

holes west of the landfill site along the Big River and 

noted orange seeps along the Big River northeast of 

the landfill. Based on a literature search and a site 

reconnaissance, they concluded that shallow ground 

water in the bedrock beneath and adjacent to the landfill site discharged into the Big River and did not enter 

the regional flow system.

As a result of a proposed expansion of the landfill in 1986, the Missouri DEQ requested a groundwater monitoring network be installed. Six monitoring 

wells were installed in the tailings (MW-101, MW102, MW-103, MW-104, and MW-105; fig. 5) and 

the Big River alluvium (MW-106) in 1987 (Geotechnology, Inc., St. Louis, Missouri, written commun., 

1987). Based on preliminary water-level data collected 

in early 1987, leachate that originated from the landfill 

would migrate along the buried Mine-A-Joe Creek 

valley northeast toward the Big River. A ground-water 

monitoring plan based on the preliminary data from 

these six monitoring wells was developed by the St. 

Francois County Environmental Corporation and

Introduction 9
52'35"

37-52'25"

90'33'

I

32'50"

r~

32-4011 90'32'30" 

I

MW-100 -f i

2,000 FT x^MW-101

A

MW-106 ' -.

\ MW-102 

P-2^^MW-109 

'MW-107

MINE-A-JOE CREEK 

DOWNSTREAM

201-P,O

wall

^Landfill 

\ Domestic i office ^ * \ well * 5y/* 

I \ 200 teat

300

I

600

I

900 FEET

100 200 300 METERS

BIG RIVER

DOWNSTREAM i

SEEP H( 

MW-104 <

SURFACE-WATER SITE AND NAME 

SEEP AND IDENTIFIER

MONITORING WELL OR PIEZOMETER 

COMPLETED IN TAILINGS OR ALLUVIUM 

AND IDENTIFIER

DOMESTIC OR MONITORING WELL 

COMPLETED IN MINE CAVITY 

AND IDENTIFIER

-- ROAD

204-P O PIEZOMETER COMPLETED IN SHALLOW 

BEDROCK AND IDENTIFIER

APPROXIMATE BOUNDARY OF THE 

OLD DESLOGE CITY DUMP

Figure 5. Sampling sites at the St. Francois County Landfill site, Missouri.

10 Hydrogeology and Water Quality at the St. Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
approved by the Missouri DNR in September 1987. 

The first water-quality samples were collected in January 1988, and monitoring has continued thereafter.

In late 1988, inspectors from the Missouri DEQ 

observed an orange seep emerging from the base of 

the tailings and a bedding plane in the bedrock at the 

entrance of the diversion tunnel. This seep (seep H, 

fig. 5) is less than 25 ft from the seep emerging from 

the concrete tunnel, sampled by the Missouri DEQ in 

1980. Analysis of a sample from seep H indicated 

large concentrations of Iron (Fe; 3,500 ug/L), manganese (Mn; 5,600 ug/L), and Zn (12,000 ug/L).

The USEPA conducted a Preliminary Site 

Assessment (PSA) and a Listing Site Inspection (LSI) 

of the 600-acre Desloge tailings pile in 1988 and 1990 

(Ecology and Environment, 1991). Results of these 

investigations determined the Desloge tailings pile 

posed a substantial risk to the environment because of 

the transport of Pb-rich materials from the site by wind 

and water. Neither the landfill nor ground-water quality was evaluated during the PSA or LSI process. 

Based on results from the LSI, the Desloge tailings 

pile was placed on the National Priorities List on 

October 14,1992. Currently (1994), the USEPA is 

evaluating strategies to control the release of tailings 

into the environment.

Rao (1991) determined that substantial quantities of Pb could be leached from tailings by landfill 

leachate. A synthetic landfill leachate (pH about 4.5) 

was constructed using acetic acid, sodium acetate, ferrous sulfate, glycine, pyrogallol, and pyrogallol-iron 

complex and was interacted with tailings from the 

landfill site in a packed column. The synthetic leachate 

mobilized substantial quantities of Pb and Zn within 1 

hour after saturation of the column; however, the solution concentrations decreased thereafter. The decrease 

in Pb and Zn concentrations with time was interpreted 

to be the result of re-sorption or re-precipitation onto 

sediments farther down the column. Based on the 

quantity of Pb leached from the tailings samples during USEPA Toxicity Characteristic Leaching Procedure (TCLP) tests, Rao (1991) concluded the tailings 

could be classified as a hazardous waste.

The USGS began a hydrochemical investigation 

in the Old Lead Belt in 1988 (Smith and Schumacher, 

1991,1993). This investigation focused on the quality 

of surface water and sediment in the Big and Flat Rivers. Water-quality samples were collected from seven 

stream sites and four seeps from tailings piles in the 

area. In addition, the flowing drill hole west of the

landfill previously sampled by the Missouri DGLS in 

1980 was sampled. Although no seeps were sampled 

routinely at the Desloge tailings pile, Mine-A-Joe 

Creek downstream of the diversion tunnel (referred to 

as the Desloge tunnel seep by Smith and Schumacher, 

1991) was routinely sampled, and a water-quality sample from a seep along the Big River downslope of 

monitoring well MW-106 (seep K, fig. 5) was collected during a seepage run and water-quality reconnaissance along the Big River in November 1989. The 

sample from seep K had a specific conductance of 

1,770 uS/cm [microsiemens per centimeter at 25 °C 

(degrees Celsius)] and anomalously large sodium (Na) 

and chloride (Cl) concentrations [62 and 76 mg/L 

(milligrams per liter)] as compared to concentrations 

of those elements in other seeps in the region. Based 

on water-quality and discharge data collected from the 

Big River upstream and downstream of the Desloge 

tailings pile, Smith and Schumacher (1993) concluded 

that most of the increase in flow and changes in water 

quality in the Big River downstream of the pile could 

be attributed to inflow from the abandoned mine cavities.

Acknowledgments

The authors are grateful to the operator and 

other personnel of the St. Francois County Landfill for 

access to heavy equipment and repair facilities. Special acknowledgment is given to Alan Aubishon of the 

St. Francois County Landfill and Marvin Hudwalker 

of Hudwalker and Associates Incorporated for their 

help in obtaining access to historical data and preparation of drill sites. The authors give special thanks to 

Ron Warren of the Park Hills Water Department for 

his technical assistance and access to well information 

and water-level records. The authors are indebted to 

the staff of the Goggins Drilling Company and many 

citizens of St. Francois County for access to their 

wells and historical information.

METHODS OF INVESTIGATION

There were three phases to the USGS investigation of the St. Francois County Landfill. The first 

phase included an information search, preliminary 

reconnaissance of the landfill site and Desloge tailings 

pile, and a well inventory to provide information on 

the direction of regional ground-water flow. The second phase of the investigation involved a detailed

Methods of Investigation 11
reconnaissance of the site and screening sampling of 

seeps for values of pH, specific conductance, and temperature and concentrations of constituents commonly 

associated with landfill leachate such as Cl, total 

ammonia as nitrogen (NH3t), total nitrite plus nitrate 

as nitrogen (NO2+NO3t), Fe, and ferrous iron (Fe2+) 

using a portable spectrophotometer. Based on screening results, reconnaissance water-quality samples were 

collected from selected seeps, in addition to the landfill supply well (landfill well, fig. 5), and existing monitoring wells. A reconnaissance of regional water 

levels also was conducted during phase II. Based on 

the results of phase I and II investigations, a monitoring-well-network plan and sampling plan were prepared and submitted to the Missouri DEQ for approval 

before initiating phase III. During phase IE, 13 monitoring wells and piezometers and 2 temporary piezometers were installed to supplement the existing 

ground-water monitoring network at the landfill site. 

Water-quality samples were collected from these additional monitoring points, the original monitoring 

wells, the Big River, selected seeps, and several 

domestic and public-supply wells in the vicinity of the 

landfill for analyses of an extensive list of physical 

properties and chemical constituents. This report, 

which concludes phase III, presents and interprets 

hydrologic and water-quality data collected throughout this investigation.

Information Search and Well Inventory

Information on the history of the landfill was 

obtained from records at the Missouri DEQ, Solid 

Waste Management Program in Jefferson City; the 

Missouri DGLS in Rolla; Hudwalker and Associates 

Incorporated, Farmington, Missouri; and the St. Francois County Landfill. Additional information was 

obtained from interviews with former mining employees, landfill employees, local water-well drilling contractors, and local citizens. Preliminary information on 

regional ground-water flow and water quality was 

obtained from published reports by Robertson (1963), 

Gann and others (1976), Imes (1990a, 1990b), Missouri Department of Natural Resources (1991), Smith 

and Imes (1991), and Imes and Emmett (1994). Waterquality data from the landfill site and surrounding area 

were obtained from records at the Missouri DEQ, 

Ecology and Environment (1991,1992,1993), Imes 

and Davis (1991), and Smith and Schumacher (1991, 

1993).

A total of 81 wells was inventoried between 

1992 and 1994 to obtain information on regional 

ground-water flow. The initial process involved a 

search of the drillers' log file and computer files of 

Missouri DGLS, Wellhead Protection Section for 

domestic and public-supply wells in St. Francois 

County. Wells within a 4- to 5-mi radius of the landfill 

were selected for possible inclusion in the well inventory. Because much of the information in these files 

cannot be verified, an attempt was made to visit well 

sites and obtain water-level, specific conductance, and 

temperature measurements. Two trips were made to 

the area during the fall of 1991 (preliminary reconnaissance) and 1992. Each onsite visit consisted of an 

interview with the well owner to obtain well completion data or driller's name, and water-level, specific 

conductance, and temperature measurements. The 

water level was measured to the nearest foot using a 

steel tape or a calibrated electric tape. For locations 

where surveyed altitudes were available or increased 

accuracy was required, water-level measurements 

were made to the nearest 0.01 ft. After measuring the 

water level, an outside faucet was turned on and water 

was allowed to flow for 10 to 15 minutes or until specific conductance and temperature measurements stabilized [plus or minus (±) 2 percent for specific 

conductance and within 0.5 °C for temperature] before 

the measurements were recorded. Specific conductance and temperature were measured using a specific 

conductance meter with temperature compensation 

designed to express values in microsiemens per centimeter at 25 °C. Meters were calibrated at least daily 

using standards bracketing the expected value for the 

water obtained from the USGS Water Quality Laboratory in Ocala, Florida. Before leaving the well site, the 

location and land-surface altitude were estimated 

using a 7.5-minute series USGS topographic map.

Monitoring Well and Piezometer Installation

Monitoring wells at the site use the prefix of 

MW- followed by a three-digit number. Piezometers 

are designated by a three- or four-digit number followed by the suffix -P. The 100-series monitoring 

wells and piezometers are completed in the tailings. 

The 200- and 2000-series piezometers are completed 

in the bedrock, and the 300-series monitoring wells 

are completed in the abandoned mine cavities. Monitoring well MW-109 was intended to be completed in 

the bedrock; however, debris (cast iron) encountered

12 Hydrogeology and Water Quality at the St. Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
in the upper alluvium prevented further drilling, and 

the screen was set to intersect the contact between the 

tailings and the Big River alluvium. Completion data 

for monitoring wells, piezometers, and temporary piezometers at the site are listed in table 1 and locations 

are shown hi figure 5.

Monitoring well MW-100 and piezometer 108- 

P were completed using a CME-75 1 drill rig and 8.25- 

in. inside-diameter (ID) hollow stem augers. Monitoring wells MW-107 and MW-109 were completed 

using an air rotary drill rig and an 8-in. diameter casing advancer. After the installation of the well and 

grout, the casing was pulled. Because of problems 

with tailings entering the auger flights, two 5-ft long, 

0.01-in. slot prepacked polyvinyl chloride (PVC) 

screens were used for monitoring wells and piezometers scheduled to be completed in the tailings (MW100, MW-107, and 108-P). No glue, cements, or sealers were used during monitoring well and piezometer 

installation.

Following installation of the screen, riser, and 

filter pack, a 1- to 3-ft thick annular seal of bentonite 

chips was placed above the filter pack and allowed to 

hydrate at least 3 hours. The remaining annulus above 

the bentonite annular seal was filled with Enviroplug 

grout using a grout pump and a side discharge tremie 

pipe. Monitoring wells and piezometers were developed by surging mechanically for 1 to 2 hours followed by pumping.

Bedrock piezometers 2020-P, 2021-P, 2022-P, 

and 2023-P were installed using an air rotary drill rig 

with a 6-in. diameter bit and a casing advance system. 

A 6-in. diameter steel surface casing was advanced 

behind the bit through the tailings about 3 ft into bedrock. The steel casing was pressure grouted in place 

using neat cement in piezometers 2020-P and 2021-P. 

After the cement was allowed to cure for a minimum 

of 24 hours, the rest of the hole was drilled. The steel 

casing in piezometers 2022-P and 2023-P was not 

grouted into place and was removed after the PVC 

screen and riser was installed and grouted.

A USGS 15-minute quadrangle map (dated 

1905) and a series of auger borings through the tailings were used to establish the configuration of the 

original (premining) land surface beneath the tailings 

at the landfill site. With one exception, the auger bor1 Use of product names in this report is for identification purposes only and does not constitute endorsement by the U.S. Geological Survey.

ings penetrated the tailings and were drilled to refusal 

(presumed to be the top of weathered bedrock) using 

3-in. ID hollow stem augers and a soil exploration drill 

rig. The altitude of the original land surface beneath 

the tailings pile and location of drill holes and mined 

areas were compiled using a geographic information 

system (GIS). Temporary piezometers (P-l and P-2, 

fig. 2) were completed in two of the auger borings 

using 1.0-in. diameter schedule-40 PVC riser with 

glued joints and a 5-ft, 0.010-in. slotted screen.

Water and Soil Sampling Methods

Water-level measurements in monitoring wells 

and piezometers at the landfill site were made using a 

steel tape calibrated in 0.01-ft increments before the 

collection of water-quality samples. The tape was 

rinsed with deionized water before each use. Waterquality samples from monitoring wells and piezometers at the landfill site were obtained using a 2-in. 

diameter stainless steel submersible pump or bailers. 

Before 1991 the existing monitoring wells at the site 

(MW-101, MW-103, MW-104, MW-105, and MW106) were sampled using disposable polyethylene 

bailers (MW-102 never contained water and was 

abandoned). The bailers were lowered slowly to minimize aeration of the water during sampling and avoid 

disturbing sediments below the screen. After 1991 all 

monitoring wells and piezometers, except those with 

2-in. diameter schedule-80 PVC risers (MW-109, 

201-P, 204-P, and 208-P) were sampled with a 

Grundfos Rediflow stainless steel submersible pump 

fitted with a polyethylene hose. Monitoring wells and 

piezometers with 2-in. diameter schedule-80 PVC 

riser were sampled using dedicated PVC bailers. Wells 

and piezometers were purged before sampling. During 

purging, specific conductance, pH, temperature, and 

dissolved-oxygen concentrations were monitored in a 

closed beaker, and water-quality samples were not collected until these measurements stabilized. Stabilization criteria were as follows: specific conductance, 

within 2 percent; pH, within 0.02 unit; temperature, 

within 0.1 °C; and dissolved oxygen, within 0.05 

mg/L. A minimum of two pipe-volumes of water was 

removed from each well before sampling. Piezometer 

2021-P recovered slowly, requiring more than 24 

hours, and water-quality samples were collected after 

purging only one pipe-volume.

The landfill well and domestic wells were sampled from the faucet closest to the well. Water from the

Methods of Investigation 13
Table 1. Completion data for landfill wells and piezometers, St. Francois County Landfill site, Missouri 

[mp, measuring point; -, not applicable; SH, schedule; PVC, polyvinyl chloride; <, less than]

I HydrogeologyQ>

Q.

1

e

SL

£(D

 n

io

2.(0

Ooc

r~

Q>Q.

Q> 3

Q.o'5|

COo1iff

33T

8

C 

T

Well 

(fig. 5)

MW-100

MW-1012

MW-1022

MW-1032MW-1042MW-1052MW-1062

MW-107

108-P

MW-109

201-P

204-P

205-P

208-P

2020-P

2021-P

2022-P2023-PMW-303Landfill well3P-lP-2

Land 

surface 

(feet)

782780784796

784

768

683

783.%

759.9

783.24779.34785.45765.7760.91781

791

785

762

7%.25788760779

Altitude 

of mp 

(feet)

783.3782.03786

796.19785.88769.78683.1

786.61

762.93

786.4

781.84

788.72768.08762.39

783.77793.19

788.19

765.05

799.25789.4

763

782.38

Bottom 

of hole 

(feet below 

land 

surface)

71.537.5

48.5

29.5

4529

10.4

103

52.5

114

84.3

80

7471.4

95.95

86.5

80.7

67.6

231

215

48

61.5

Bottom Top of 

of well bedrock 

(feet below (feet below 

land land 

surface) surface)

70.0

36.4

48.0

29.54329

10.1

103

52.1

107.9

77.9

78.9

64.4

70.8

94.4

86.079.7

65.9

231

215

37.7

59.3

37.5

29.5

4529

~

102

52.5

..

15

46

17.5

50.5

28.2

21

4.0

15

23

<10

49.0

Top of Bottom of 

filter pack filter pack 

(feet below (feet below 

land land 

surface) surface)

56.520.427

3.5

27

16.7

3

87

37.2946565.551

58.4

81

71.567.3

51.6- 53.0

67.5

37.5

48.5

29.545

29

10.4

103

52.1

108.5

80.180

69

71.495.9586.48

80.7

67.6-_ 61.5

Top of 

screen 

(feet below 

land 

surface)

! 59.6

21.4

28

4.5

28

19

5.1

! 91.8! 41.7

97.5

67.568.5

5460.4

84

75.669.355.5

..- 32.5

54.3

Casing 

diameter Casing 

(inches) type

2

2

2

22

2

242

22

2

2

2

22

22

4

6

11

SH40 PVC

SH40PVC

SH40PVCSH40PVC

SH40PVC

SH40 PVCSH40PVCSH40PVCSH40PVC

SH80 PVC

SH80 PVC

SH80 PVCSH40PVCSH80 PVCSH40PVCSH40PVCSH40PVCSH40 PVC

SH40PVCSH40PVC

SH40PVCSH40PVC

Top annular 

seal 

(feet below 

Filter land 

type surface)

WB35

WB40

WB40WB40

WB40

WB40

WB40

WB 10-20WB 10-20WB 10-20

WB 10-20WB 10-20

WB 20-40

WB 10-20WB 10-20WB 10-20

WB 10-20WB 10-20

~_ WB20

54.5

19.4

26

2.5

26

15.7

0

85

3491

63

615057.27667.2

66

49.15

~

35

Surface 

casing 

(feet below 

land 

surface)

..~-~-~-..

~

55

~

53

28

29

~

188

80_ 1 Prepacked screen.

2 Well installed by Geotechnology, Inc.

3 Data obtained from Goggins Drilling Company (written commun.. 1992).
faucet was allowed to flow freely, and specific conductance, pH, temperature, and dissolved-oxygen concentrations were monitored in a closed beaker. Municipal 

wells were sampled in a similar manner from a tap at 

the wellhead.

Discharges of seeps were measured or estimated; measurements of specific conductance, pH, 

temperature, and dissolved oxygen were made directly 

at the seep orifice. Seeps were sampled by placing a 

clean 500-mL (milliliter) polyethylene bottle below 

the orifice or digging a small hole to form a pool in 

which the bottle could be immersed. The bottle was 

filled and contents emptied into a churn splitter until a 

sufficient volume was collected. Samples for volatile 

organic compounds (VOC) were collected by filling 

each 40-mL VOC vial directly from the seep. No 

seeps were sampled for pesticides.

Discharge and water quality were determined 

for streams at the landfill site. Stream discharges were 

measured using a standard AA current meter or a 

pygmy current meter according to the methods 

described by Rantz and others (1982). Where streamflow was not sufficient for the above methods, the discharge was estimated. Discharge measurements and 

water-quality samples were collected from the Big 

River upstream of the landfill by wading several feet 

upstream of a low-water crossing referred to locally as 

the "Bone-hole." Discharge measurements and waterquality samples were collected downstream of the 

landfill by wading a narrow section of the Big River 

approximately 100 ft downstream of monitoring well 

MW-106. Depth integrated water-quality samples 

were collected using a hand-held DH-48-TM sampler 

(Ward and Harr, 1990). A minimum of 10 separate 

subsamples was collected at equal-width intervals 

across the stream and composited using a churn splitter. Where flow conditions were not sufficient to use a 

DH-48-TM, grab samples from the centroid of flow 

were made using a 500-mL polyethylene bottle and 

composited in a churn splitter. Values of specific conductance, pH, and temperature and dissolved-oxygen 

concentrations were measured directly in the stream 

near the centroid of flow and in a subsample from the 

churn splitter. Samples for VOC were collected from 

the Big River by filling the vials directly from the centroid of flow. No pesticide samples were collected 

from the Big River.

The specific conductance of water samples was 

measured using a portable specific conductance meter 

with temperature compensation designed to express

values in microsiemens per centimeter at 25 °C. The 

meter was calibrated before each measurement using 

standards prepared by the USGS Water Quality Laboratory in Ocala, Florida. The pH was measured using a 

portable pH meter calibrated with standard buffers 

bracketing the expected sample pH before each measurement. Temperature was measured to the nearest 

0.1 °C using a thermistor attached to the pH meter. 

Dissolved-oxygen concentrations were determined by 

colorimetry to the nearest 0.05 mg/L using a diethylene glycol and rhodazine-D method. This method was 

applicable for concentrations of dissolved oxygen 

ranging from 0.05 to 1.0 mg/L. An indigo carmine 

method was used for concentrations greater than 1 

mg/L. Total alkalinity [Alk(IT)] was determined by 

using incremental titration of 0.16 normal standardized sulfuric acid into 25 mL of sample past the carbonate-bicarbonate inflection point (approximately pH 

8.3) and the bicarbonate-carbonic acid inflection point 

(approximately pH 4.5). Concentrations of carbonate 

(CO3), bicarbonate (HCO^), and CO3 alkalinity were 

later computed using a computer program to integrate 

the rate of pH change to the equivalence of acid added.

Inorganic chemical constituents referred to as 

"dissolved" were filtered through a disposable capsule 

filter comprised of a 0.45-|im (micrometer) pore-size 

polysulfone filter encased in a polycarbonate housing. 

Samples from monitoring wells and piezometers collected with the submersible pump were filtered by 

decreasing the pumping rate to less than 500 mL per 

minute and fitting the filter to the end of the pump 

hose. Samples from all other locations were filtered 

after collecting several liters of water in a churn splitter (glass bottle for organic constituents) for transport 

to a vehicle where aliquots were filtered using a disposable capsule filter and a peristaltic pump. Before 

1993, samples were filtered through a 142-mm (millimeter) diameter, 0.45-|im pore size cellulose-nitrate 

membrane filter placed in a leucite holder. A peristaltic pump was used as the pressure source for filtration. 

Samples for dissolved cations were collected in acidwashed polyethylene bottles directly from the filter 

outlet and preserved with nitric acid to a pH less than 

2. Samples for dissolved anions were placed into clean 

polyethylene bottles. Samples for dissolved nutrients 

[nitrogen (N) and phosphorous (P) species] were 

placed in amber polyethylene bottles, preserved by 

adding 1 mL of 10"4 molar mercuric chloride, and 

chilled to 4 °C. Samples for total recoverable cations 

from monitoring wells and piezometers were collected

Methods of Investigation 15
in acid-rinsed polyethylene bottles directly from the 

pump outlet, bailer, or churn splitter and acidified to a 

pH less than 2 with nitric acid. Samples for chemical 

oxygen demand (COD) were collected in 250-mL 

glass bottles and preserved with 1 mL sulfuric acid. 

Total organic carbon (TOC) samples were collected in 

250-mL amber glass bottles and preserved by chilling 

to 4 °C. Samples for tritium determinations were collected in 1-L (liter) glass bottles filled from the bottom 

using a silicon hose to exclude any contact with the 

atmosphere. Inorganic constituents and tritium determinations were made according to the methods 

described by Fishman and Friedman (1989). Concentrations of inorganic constituents and determinations 

of COD and TOC were made according to the procedures outlined in Fishman and Friedman (1989) and 

Wershaw and others (1983).

Samples for the determination of VOC were 

collected in 40-mL amber glass vials with a Teflon 

septum cap. Each sample consisted of six vials: two 

vials acidified to pH of 2 with 12 normal organic-free 

hydrochloric acid (HC1), two vials acidified to pH 5 

with 3 normal organic-free HC1, and two vials unpreserved. After preservation the vials were chilled to 4 

°C and shipped overnight to the USGS National Water 

Quality Laboratory in Arvada, Colorado. Concentrations of VOC were determined using purge and trap 

capillary gas chromatography/mass spectrometry 

(GC/MS) according to USEPA method 524.2 (U.S. 

Environmental Protection Agency, 1983). The VOC 

targeted were those required under assessment monitoring of sanitary landfills (Code of Federal Regulations, 1992), in addition to a number of other VOC. A 

complete list of the target and nontarget VOC, detection levels, and selected USEPA drinking water regulatory limits is given in table 2.

Samples for total organic halogens (TOX) were 

collected in baked 1-L amber glass bottles with Teflon 

septum caps. The samples were acidified to pH 2 with 

36 normal sulfuric acid, chilled to 4 °C, and shipped 

overnight to a contract laboratory in St. Louis, Missouri. Analyses were performed using carbon adsorption with a microcoulometric-titration detector. The 

method is sensitive to dissolved organic halides containing chlorine, bromine, and iodine that are absorbed 

by granular activated carbon. Concentrations of TOX 

are reported as micrograms per liter chlorine.

Samples were collected in September 1993 for 

analysis of selected pesticides. Pesticide samples were 

filtered through a 142-mm diameter 0.7-jim pore size

baked glass-fiber filter placed in an aluminum holder. 

A fluid-metering pump was used as the pressure 

source. The filter holder and all hoses were rinsed with 

a 10 percent non-phosphate detergent solution, triple 

rinsed with organic-free water, and rinsed with ultrapure methanol between each site. The filtrate was 

placed in a 1-L amber, baked-glass bottle and chilled 

immediately. Pesticide determinations were made by 

GC/MS using solid-phase extraction techniques 

described by Thurman and others (1990). The list of 

target pesticides, detection levels, and selected USEPA 

drinking water regulatory limits is given in table 2.

Soil and tailings samples were collected using a 

2-in. diameter stainless steel split spoon during the 

installation of monitoring wells MW-100 and MW107 and piezometer 108-P. Samples were placed into 

1-L wide-mouth jars and shipped to the USGS 

geochemistry laboratory in Denver, Colorado. Bulk 

mineralogic and chemical analyses were performed 

according to procedures described in Starkey and others (1984), Taggart and others (1987), and Davis 

(1988).

Equipment blanks were collected at the conclusion of each sampling trip. Organic- and inorganicfree water was pumped through the submersible pump 

and hose and processed in a similar manner to groundwater samples. Concentrations of major inorganic constituents were less than 0.5 mg/L, and concentrations 

of nutrients were less than 0.01 mg/L in all blanks. 

Several blanks contained detectable concentrations of 

dissolved Fe (less than 3-5 jug/L), total iron (Fet; 20- 

60 ug/L), Pbt (3-4 jig/L), and total manganese (Mnt; 

less than 1-6 ug/L). Except for one VOC blank collected in April 1993, none of the blanks contained 

detectable concentrations of VOC. Detections in the 

April 1993 blank were traced to contaminated HC1 

used to preserve the blank sample.

GENERAL CHARACTERISTICS OF 

MUNICIPAL SOLID WASTE AND 

LEACHATE PRODUCTION

Before regulatory legislation, most municipal 

solid waste in the United States was contained in open 

dumps. The exposed waste created public concern, 

and sanitary landfills became the predominant method 

of waste disposal. Sanitary landfills require excavating 

cells of overburden, filling the cell with waste, and 

covering with soil.

16 Hydrogeology and Water Quality at the St. Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
Table 2. Detection levels and drinking water regulatory limits for organic compounds

[Hg/L, micrograms per liter, MCLG, maximum contaminant level goal; MCL, maximum contaminant level; DWEL, drinking water equivalent level; 

<, less than; , no data]

Drinking water regulatory limits1

Detection level

Chemical family Organic compound

MCLG 

(M9/L)

MCL DWEL

Substituted methane

Substituted ethane

Substituted ethene

Substituted propane

Substituted propene

Bromomethane

Dibromomethane

Bromoform

Bromochloromethane

Dibromochloromethane

Chloromethane

Dichloromethane

Trichloromethane (chloroform)

Carbon tetrachloride

Chlorofluoromethane2

Dichlorobromomethane

Dichlorofluoromethane2

Dichlorodifluoromethane

Trichlorofluoromethane

Methyl iodide

Carbon disulfide (CS2)

Chloroethane

1,2-Dibromoethane (EDB)

1.1-Dichloroethane (DCA)

1.2-Dichloroethane

1.1.1-Trichloroethane (TCA)

1.1.2-Trichloroethane 

1,1,1,2-Tetrachloroethane 

1,1,2,2-Tetrachloroethane 

Trichlorotrifluoroethane 

Vinyl chloride (VC) 

1,1-Dichloroethene (1,1-DCE) 

cis-l,2-Dichloroethene (cis-DCE) 

trans-l,2-Dichloroethene (trans-DCE) 

1,1,2-Trichloroethene (TCE) 

1,1,2,2-Tetrachloroethene (PCE) 

1,2-Dichloropropane 

1,2,3-Trichloropropane 

l,2-Dibromo-3-chloropropane (DBCP) 

cis-1,3-Dichloropropene 

trans-1,3-Dichloropropene

Volatile organic compounds

<0.2

<2

0

200

3

100

100

.05

5

200

5

.2

40

700

0

0

0

0

100

-

5

100

5

700

100

2,000

400

30

700

5,000

1,000

100

1,000

0

7

7

100

0

0

0

5

7

70

100

5

5

5

-

400

400

600

300

500

200

General Characteristics of Municipal Solid Waste and Leachate Production 17
Table 2. Detection levels and drinking water regulatory limits for organic compounds Continued

Drinking water regulatory limits1

Chemical family Organic compound

Detection level

OiO/L)

MCLG 

(ug/L)

MCL

OiO/L)

DWEL 

(ug/L)

Substituted butene 

Benzene derivitives

Ether

Volatile organic compounds Continued

trans-l,4-Dichloro-2-butene <1.0

Benzene <.2

Chlorobenzene <.2

1.2-Dichlorobenzene <.2

1.3-Dichlorobenzene <.2

1.4-Dichlorobenzene <.2

Ethylbenzene <.2

Xylenes (total) <.2

Styrene <.2

Toluene <.2

Napthalene2 <.2

2-Chloroethylvinylether <.2 

Methyltertiarybutyl ether (MTBE) <.2

Aldehyde

Ketone

Ester

Nitrite

Acetanilide

Amide

Benzamide

Benzenamine

Carbamate

Carbothioate

Ethyl ether2

Acrolein

Acetone

2-Butanone (Methyl ethyl ketone)

2-Hexanone (Methyl butyl ketone)

4-Methyl-2-pentanone (MIBK)

Vinyl acetate

Acrylonitrile

Alachlor

Napropamide

Propanil

Pronamide

Ethalfluralin

Butylate

Carbaryl

Carbofuran

s-Ethyldipropylthiocarbamate (EPTC)

Pebulate

Thiobencarb

Molinate

<.2

<20

<5

<20

<20

<20

<20

<20

Pesticides

<0.009

<.01

<.016

<.009

<.013

<.008

<.046

<.013

<.005

<.009

<.008

<.007

0

100

600

600

75

700

10,000

100

1,000

40

5

100

600

600

75

700

10,000

100

1,000

40

700

3,000

3,000

4,000

3,000

60,000

7,000

7,000

100

200

400

3,000

2,000

4,000

200

18 Hydrogeology and Water Quality at the St. Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
Table 2. Detection levels and drinking water regulatory limits for organic compounds Continued

Drinking water regulatory limits1

Chemical famiiy Organic compound

Detection level MCLG 

Oig/L) (ng/L)

MCL DWEL 

Oig/L) (jig/L)

Pesticides Continued

Chloracetanilide

Cyclohexane

Dichloroethylene

Dinitroaniline

Methyluracil

Napthalene

Organophosphate

Organophosphorus

Phosphonodithioate

Phosphorothioate

Pyrethroid

Substituted urea

Sulfite ester

Terepthalate/dimethyl

Thiocaramate

Toluidine

Triazine

Triazinone

Metolachlor

Propachlor

Alpha benzenehexachloride (BHC)

Lindane

2,6 Diethylaniline

p,p'-Dichlorodiphenyldichlrorethylene(DDE)

Pendimethalin

Trifluralin

Terbacil

Dieldrin

Ethoprop

Malathion

Methyl parathion

Parathion

Phorate

Terbufos

Disulfoton

Methyl azinphos

Fonofos

Dimethoate

Chlorpyrifos

Diazinon

Permethrin

Linuron

Tebuthiuron

Propargite

Dimethyl tetrachloroterephtalate (DCPA)

Triallate

Benfluralin

Atrazine

Cyanazine

Desethyl atrazine

Prometon

Simazine

Metribuzin

<0.009

<.015

<.007

<.011 0.2

<.006

<.01

<.018

<.012

<.03

<.008

<.012

<01

<.035

<.022

<.011

<.012

<.008

<.038

<.008

<.024

<.005

<.008

<.016

<.039

<.015

<.006

<.004

<.008

<.013

<.017 3

<.013 1

<.007

<.008

<.008 4

<.012

5,000

500

--

0.2 10

--

-

-

300

400

2

--

800

9

--

-

5

1

--

70

-

100

-

-

-

2,000

-

4,000

..

-

3 200

70

200

500

4 200

900

1 U.S. Environmental Protection Agency (1993).

2 Non-target compound, estimated detection level.

General Characteristics of Municipal Solid Waste and Leachate Production 19
Waste Composition Waste Degradation and Leachate Production

Tchobanoglous and others (1977) reported the 

typical composition of municipal solid wastes in percent by weight of the most readily identified components (table 3). Nearly 80 percent of typical solid 

waste is made of cellulose and will decompose readily. 

The remaining 20 percent degrades extremely slowly. 

The rate and degree of initial decomposition depends 

on the amount of moisture present in the material. 

Moisture content is important in determining whether 

the degradation process is predominantly aerobic or 

anaerobic. The components of the waste also affect the 

amount of water available for degradation processes. 

For example, if the waste contains large amounts of 

food, it has a greater moisture content; with large 

amounts of paper, moisture is absorbed. Moisture content of typical municipal solid waste is reported in 

table 3.

Table 3. Typical physical composition of municipal solid 

waste and moisture content of waste components

[--, no data; modified from Tchobanoglous and others (1977)]

Percent 

composition 

(by weight)

Moisture

content

(percent by

weight)

Component Range Typical Range Typical

Food wastes

Paper

Cardboard

Plastics

Textiles

Rubber

Leather

Garden trimmings

Wood

Glass

Tin cans

Nonferrous metals

Ferrous metals

Dirt, ashes, and brick

Municipal solid wastes

6-26

25-45

3-15

2-8

0-4

0-2

0-2

0-20

1-4

4-16

2-8

0-1

1-4

0-10

-

15

40

4

3

2

.5

.5

12

2

8

6

1

2

4

-

50-80

4-10

4-8

1-4

6-15

1-4

8-12

30-80

15-40

1-4

2-4

2-4

2-6

6-12

15-40

70

6

5

2

10

2

10

60

20

2

3

2

3

8

20

(composite of above components)

After burial, waste is affected by several processes, including biological decay, dissolution, precipitation and sorption of chemical constituents, leaching 

of sediments, ion exchange, generation and diffusion 

of gases, and movement of dissolved materials. Degradation processes depend on the composition of the 

waste, the degree of sorting and compaction, moisture 

content, and temperature. The rate of microorganism 

activity is controlled by temperature, oxygen availability, and type and availability of organic material 

(Baedecker and Back, 1979). The largest number of 

microorganisms grow in buried waste when the temperature ranges from 15 to 30 °C (Dobson, 1964). The 

degradation phases of typical municipal solid waste 

are delineated by the gas composition in the landfill 

cell and by the concentrations of chemicals in the 

landfill leachate (fig. 6).

The easily degradable components of waste, 

such as food and yard waste, are subject to aerobic 

decomposition almost immediately after burial. This 

occurs in an oxidizing environment, represented by 

phase 1 shown in figure 6. The end products of aerobic 

degradation are carbon dioxide (CO2), water, sulfate 

(864), and ammonia as nitrogen (NR3; Baedecker and 

Back, 1979). Aerobic degradation may be complete in 

a few days or weeks (Tchobanoglous and others, 

1977).

Water is produced during aerobic degradation, 

thereby making a greater amount of moisture available 

for anaerobic decomposition processes. The anaerobic 

degradation processes are represented by phases 2, 3, 

and 4 (fig. 6). Anaerobic degradation produces substantial quantities of methane. The volumes of CO2, 

hydrogen (H), volatile fatty acids, NH3, SO4, and Zn 

in leachate peak during these phases. The COD peaks 

in phase 2, then decreases sharply. The CO2 derived 

from aerobic degradation readily dissolves in leachate, 

increasing the alkalinity of the leachate. During phase 

2, pH is at its lowest value and, if calcium carbonate 

(CaCO3) is present in the fill or cover, it may be dissolved by the acidic leachate. The pH value of 

leachate begins to increase gradually during phase 3 

and stabilizes in phase 4.

Anaerobic degradation processes occur rapidly. 

Methane production peaks within 2 years then 

declines for 25 years or more (Tchobanoglous and others, 1977). During phase 5, methane production 

decreases substantially, and some zones in upper landfill layers may become aerobic. Until this phase, N is

20 Hydrogeology and Water Quality at the St. Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
100

60

50

40

20

GAS COMPOSITION

Mtrogen

Carbon dioxide

Hydrogen

Nitrogen,

^ M§tharie_

LEACHATE COMPOSITION

Chemical oxygen demand

Volatile fatty acids \

pH

\ * = / / ;

LEACHATE COMPOSITION

Degradation phase

/Bicarbonate

INCREASING TIME

Figure 6. Phases of solid waste degradation and leachate production (modified from Christiansen and 

others, 1989).

General Characteristics of Municipal Solid Waste and Leachate Production 21
present mainly as NH3 from anaerobic degradation, 

but during phase 5 nitrogen gas (N2) diffuses from the 

atmosphere into the soil.

Large concentrations of inorganic constituents 

such as calcium (Ca), Na, Cl, Fe, 864, and NH3 are 

common in landfill leachate (Uhlman, 1989). The Cl 

concentration is highest during the initial stages of 

decomposition and decreases thereafter. Ideally, the 

products of complete anaerobic degradation of sanitary refuse are methane, water, and CO2 (Baedecker 

and Back, 1979). Bicarbonate is a product of anaerobic degradation and is produced when CO2 dissolves 

in landfill leachate. Bicarbonate also may come from 

ash, soil, and rock in the landfill. Sulfate produced by 

aerobic degradation processes is reduced to sulfide 

(S2~) during the anaerobic phases. The S2" may be 

removed by precipitation of insoluble sulfides, such as 

pyrite (FeS2), or evolve as hydrogen sulfide (H2S) gas. 

The presence of bacterially generated organic acids in 

leachate increases its capacity to dissolve and transport trace inorganic constituents. Acidic leachate seeping through the waste and earth materials below the 

landfill may cause some trace constituents to dissolve. 

Complexes with organic ligands also may increase 

trace constituent solubility.

The most commonly detected organic compounds are chlorinated solvents, petroleum derived 

hydrocarbons, and pesticides (Borden and Yanoshak, 

1990). Ranges of concentration of the most common 

constituents of landfill leachate from several studies 

are shown in table 4. The concentrations of various 

constituents in landfill leachate vary with the age of 

the landfill and decrease with time.

SURFACE-WATER HYDROLOGY

The Big River is the principal stream in the 

region, flowing eastward and northward through the 

Old Lead Belt (fig. 1). The USGS maintains a continuously recording gaging station on the Big River about 

15 mi upstream of the landfill site at Irondale, Missouri. The maximum recorded instantaneous discharge 

of 49,100 ft3/s (Reed and others, 1995) at this gage 

occurred on November 14, 1993, after a series of 

intense rains. The minimum recorded instantaneous 

discharge of 2.5 ft3/s (Reed and others, 1995) occurred 

on September 15,1971. The estimated 7-day 2-year 

low flow of the Big River in the vicinity of the landfill 

site is about 12 ft3/s (Skelton, 1976). A seepage run 

along the Big River during low-flow conditions in

September and November of 1989 (Smith and Schumacher, 1993) indicated the discharge of the Big River 

increased more than 10 percent in the vicinity of the 

landfill site. Most of this increase was attributed to 

inflow from the abandoned mines through flowing 

drill holes and diffuse inflow from ground-water 

sources. The principal tributary to the Big River is the 

Flat River, which enters the Big River about 3.5 mi 

downstream of the landfill site (fig. 1). The Flat River 

is an intermittent stream that gains flow along some 

reaches and may lose flow along others.

Surface-water drainage from most of the landfill 

site flows through a drainage structure near the landfill 

office and enters Mine-A-Joe Creek near the entrance 

to the diversion tunnel. Most of the runoff from this 

area is ponded upstream of the drainage structure to 

settle most suspended solids before the runoff is 

released. A small amount of drainage from the southeastern part of the landfill and southern part of the chat 

pile flows through a small culvert at the southeast corner of the landfill property near piezometer 201-P 

(figs. 2 and 5). This flow enters Mine-A-Joe Creek 

about 1,000 ft upstream of the diversion tunnel. Drainage from the northern part of the landfill site and 

northwest part of the chat pile flows into a flat area 

southwest of monitoring well MW-101. After intense 

rain in this area, runoff ponds gradually drain through 

a small ditch into the Big River west of the landfill. A 

small closed depression containing piezometer 2021- 

P collects runoff from about 10 acres of the landfill 

site and chat pile. This depression holds water for several days after an intense rain, after which the water 

infiltrates into the tailings or evaporates. Until about 

1993, a similar closed depression was immediately 

east and upslope from monitoring well MW-105.

HYDROGEOLOGY

The St. Francois County Landfill lies within the 

Old Lead Belt on the northern flank of a positive structure known as the St. Francois Mountains. The St. 

Francois Mountains are the core of a much larger 

structural feature called the Ozark Uplift, which dominates the geology of southern Missouri and northern 

Arkansas. The hydrogeology of the Old Lead Belt 

region is complex because of the structural framework, varied lithologies, and presence of extensive 

subsurface mine workings.

22 Hydrogeology and Water Quality at the St. Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
Table 4. Common constituents of landfill leachate

[All concentrations in milligrams per liter unless noted otherwise; , no data; <, less than]

Parameter

pH, in standard units

Biological oxygen demand (BOD)

Chemical oxygen demand (COD)

Total organic carbon (TOC)

Hardness

Alkalinity

Total dissolved solids (TDS)

Chloride

Ammonia

Nitrate

Phosphorus

Sulfate

Calcium

Magnesium

Potassium

Sodium

Arsenic, in micrograms per liter

Boron, in micrograms per liter

Iron, in micrograms per liter

Lead, in micrograms per liter

Manganese, in micrograms per liter

Nickel, in micrograms per liter

Zinc, in micrograms per liter

Tchobanoglous1

5.3-8.5

2,000-30,000

3,000-45,000

1,500-20,000

300-10,000

1,000-10,000

-

100-3,000

10-800

5-40

1-70

100-1,500

200-3,000

50-1,500

200-2,000

200-2,000

~

~

50-600

--

-

~

-

Cameron2

3.7-8.5

9-55,000

0-9,000

~

0-22,800

0-20,900

0-42,300

34-2,800

0-1,106

-

0-154

1-1,826

5-4,000

16.5-15,600

2.8-3,770

0-7,700

0-11.6

.3-73

.2-5,500

0-5.0

.06-1,400

.01-.8

0-1,000

Salvato3

5.6-8.3

7,050-32,400

7,130

--

500-8,700

1,290-8,100

2,000-11,254

220-2,240

141-845

5-18

--

24-1,220

--

~

655-1,860

350-1,805

-

-

219-336

-

-

~

-

Kunkle4

5.84-6.16

13,800-16,800

46,600-52,400

9,250-10,300

12,800

7,030-7,820

5,661-6,086

1,325-1,375

336-340

<.01

.01-.03

265-411

2,230

727

680

1,440

.13

~

1,510

4.9

57

.84

7.8

1 Tchobanoglous and others (1977).

2 Cameron (1978).

3 Salvato and others (1971).

4 Kunkle and Shade (1976).

Geology

The St. Francois Mountains are comprised of 

Precambrian igneous rocks, mainly rhyolitic porphyries and granites intruded by felsic and diabasic rocks. 

The porphyries and granites are the oldest rocks in the 

region. Many of the intrusive structures have been 

eroded to form knobs, some of which are exposed at 

the surface about 5 mi south of the landfill site. Other 

principle structural features in the region include the 

Simms Mountain Fault System, trending northwest 

about 5 mi southwest of the site, the Big River Fault

System about 4 mi to the northwest, and the Farmington Anticline to the northeast (fig. 7). Numerous 

steeply dipping faults with displacements of more than 

100 ft have been mapped in the Old Lead Belt (Snyder 

and Gerdemann, 1968); however, no such faults have 

been mapped within 1 mi of the landfill site.

Drill logs from public-supply wells in Leadwood and Gumbo indicate that about 550 to 700 ft of 

Paleozoic sedimentary rocks overlie the Precambrian 

rocks in the vicinity of the landfill site. Paleozoic 

rocks in the region are the Lamotte Sandstone, BonHydrogeology 23
90'37'30 38'

52'30"

37'45'

90'22'30"

I I MINED AREA OF THE OLD LEAD BELT 

E3 POTOSI DOLOMITE

DERBY-DOE RUN DOLOMITE

DAVIS FORMATION

BONNETERRE FORMATION

LAMOTTE SANDSTONE

PORPHYRY 0 1 2 KILOMETERS

GRANITE

FAULT TRACE

DOMESTIC OR PUBLIC-WATER-SUPPLY 

WELL IN REGIONAL INVENTORY

Rgure 7. Regional geology in the vicinity of the St. Francois County Landfill site, Missouri (geology 

modified from Buckley, 1908).

24 Hydrogeology and Water Quality at the St. Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
neterre Formation, Davis Formation, Derby-Doe Run 

Dolomite, and Potosi Dolomite2 (fig. 8).

The Lamotte Sandstone is the oldest Paleozoic 

rock in the region and unconformably overlies the Precambrian rocks. The formation crops out along the 

south side of the Simms Mountain Fault System southwest of the site (fig. 7). The Lamotte Sandstone is a 

quartzose sandstone with occasional siltstone or dolomitic beds in the upper part (Snyder and Gerdemann, 

1968). The unit grades laterally into an arkose and 

conglomerate near Precambrian knobs, and in some 

localized areas, the upper part of the unit is mineralized. The thickness of the unit varies considerably in 

the region but may be as much as 500 ft in depressions 

between Precambrian knobs. Drill logs from three 

public-supply wells in Leadwood and Gumbo indicate 

the Lamotte Sandstone ranges from 120 to 275 ft 

thick.

The Bonneterre Formation crops out throughout 

a large part of the Old Lead Belt. It lies directly 

beneath the Desloge tailings pile and landfill site. This 

formation was the primary host rock for the vast Pb 

ore deposits in the Old Lead Belt. In this region, the 

Bonneterre Formation generally is a light gray, fine- to 

medium-grained, medium- to thickly bedded dolostone. Typically the Bonneterre Formation is about 

375 to 400 ft thick; however, the thickness varies considerably in the Old Lead Belt because of local structure and erosion where the formation crops out. The 

lower 100 ft contains a variety of depositional structures where the richest ore was concentrated. The middle part of the formation generally is massively 

bedded with thin shale interbeds. This part of the formation is exposed along the walls of the diversion tunnel and in bluffs along the Big River immediately 

north of the chat pile. The formation contains well 

defined joints, most trending about N. 54° W and N. 

83° W. Drill logs from public-supply wells in Leadwood and Gumbo indicate a range of thickness from 

210 to 415 ft. The contact between the Bonneterre 

Formation and Lamotte Sandstone is about 280 ft 

below the surface of the tailings pile, an altitude of 

about 500 ft.

The Davis Formation unconformably overlies 

the Bonneterre Formation. The predominant lithology 

in the Old Lead Belt is shale with interbedded carbonates and glauconitic sandstones and siltstones. A comNomenclature follows usage of the Missouri Department of 

Natural Resources, Division of Geology and Land Survey.

plete section of the Davis Formation is exposed along 

State Highway 8 about 2 mi west of the landfill site. 

Thompson and Palmer (1987) described this section in 

detail and reported the formation to be 170 ft thick. 

The unit is not present beneath the Desloge tailings 

pile or the landfill, but is exposed north and west of the 

Desloge tailings pile across the Big River.

The Derby-Doe Run Dolomite is undifferentiated in the region. The upper part is a massive oolitic 

dolostone or algal reef dolostone and the lower part is 

a thin-bedded, argillaceous dolostone with glauconite. 

The thickness of the Derby-Doe Run Dolomite ranges 

from 0 to 200 ft, but commonly is about 150 ft thick.

The Potosi Dolomite is the youngest formation 

exposed in the region. The formation is a brown, massively bedded, siliceous dolostone containing quartz 

druse, and averages about 200 ft thick. The Potosi 

Dolomite contains abundant karst features, such as 

solution channels, caves, and sinkholes.

Regional Hydrogeology

Hydrogeologic units have been defined in the 

Old Lead Belt (fig. 8). This definition was made as 

part of the USGS Central Midwest Regional AquiferSystem Analysis (Jorgenson and Signor, 1981), which 

was conducted to gain information on the flow regime 

and geohydrologic properties of regional aquifer systems in the Midwest.

The Lamotte Sandstone and Bonneterre Formation comprise the St. Francois aquifer in eastern Missouri (Imes, 1990a). The St. Francois aquifer is the 

lowermost aquifer in the Ozark Plateaus aquifer system. It is underlain by the basement confining unit that 

is composed of Precambrian rocks. The St. Francois 

County Landfill lies within the recharge area for the 

St. Francois aquifer. The aquifer is used extensively 

for domestic and public-water supply throughout the 

outcrop area in and around the St. Francois Mountains. 

The hydraulic conductivity of the aquifer was computed from specific capacity data by Imes (1990a) and 

ranges from 10"6 to 10"4 ft/s with a general decrease in 

values with distance from the St. Francois Mountains. 

Most public-supply wells are completed in the Lamotte Sandstone and lower Bonneterre Formation, and 

wells with an appreciable thickness of Lamotte Sandstone typically yield 100 to 500 gal/min (gallons per 

minute). Generally only domestic wells are completed 

in the Bonneterre Formation, and these wells yield 

about 1 to 10 gal/min.

Hydrogeology 25
ERATHEM

Paleozoic

SYSTEM

Cambrian

Precambrian

UTHOLOGIC 

COLUMN

/ /<=> /

/<=» / /<=» /

<=>/<=> /<=> /=> ' <=^/'=> /<=> /

x 5 -" / /* ' /

/<=> / /<=>

' / /* /~

/ / s /

/ / /

' / / /

/ / / /

/ / /

' / / /

/ / / /

/ / /

1 T T ~

1 1 1 1

- 1 ! 1 

/ / ' / / /

/ / / /

/ / /

/ / /

/ / / /

/ / /

/ / /

/ / / /

f-.-:--:t:-:-.-:-.:l:-:-:-:-K-

-I- -.-:-|-.-:-.- --. : 

 ^. ^ j^ii^y

^j^y/f

 . -. . . . '.- . :: .*:'- . :: .

I.'.'.:.'. . .: .- .-. .: ,-: .- »- >.

GEOLOGIC UNIT

Potosi Dolomite

Derby-Doe Run 

Dolomite

Davis Formation

Bonneterre Formation

Lamotte Sandstone

St. Francois Mountains 

(intrusive and volcanic 

rocks)

TYPICAL 

THICKNESS, 

IN FEET

75-300

0-200

0-225

375-400

0-500

Greater 

than 

4,000

UTHOLOGY

Massively bedded dolostone with 

algal reefs, recrystalized 

dolomite, and quartz druse

Massive dolostone and thin-bedded 

argillaceous dolostone

Calcareous shale with dolostone, 

limestone conglomerate, and 

limestone

Rne- to medium-grained, mediumto thickly bedded dolostone

Sandstone with occasional siltstone 

or dolomitic beds

Granite and volcanic rocks, 

including porphyry

HYDROGEOLOGIC 

UNIT

Ozark aquifer

St. Francois 

confining 

unit

St. Francois 

aquifer

Basement 

confining 

unit

Figure 8. Generalized stratigraphic column for the Old Lead Belt area, southeastern Missouri (modified from 

Smith and Imes, 1991).

26 Hydrogeology and Water Quality at the St Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
The Davis Formation and the Derby-Doe Run 

Dolomite comprise the St. Francois confining unit. 

This is the lowermost confining unit in the Ozark Plateaus aquifer system. Quantitative measurements of 

lateral hydraulic conductivity of the confining unit are 

not available; however, vertical hydraulic conductivity 

of the confining unit derived from ground-water simulations is about 10'8 ft/s (Imes and Emmett, 1994). The 

confining unit crops out throughout most of the western part of the Old Lead Belt; however, it is not 

present at the landfill site or throughout most of the 

central part of the region (fig. 7), where the St. Francois aquifer crops out.

Water levels in the Old Lead Belt have changed 

dramatically as the result of past mining activities. 

Before 1972, the mines and much of the adjacent St. 

Francois aquifer were dewatered. Just before the mine 

pumps were shut off in 1972, an estimated 14 Mgal/d 

(million gallons per day) were pumped from the mines 

(Ron Warren, Park Hills Water Department, written 

commun., 1993). This rate is comparable to a city with 

a population of about 150,000. Pumpage from the 

mines produced a large cone of depression around the 

Old Lead Belt (fig. 9). The effect of dewatering the 

mines on water levels in public-supply wells completed in the Lamotte Sandstone is shown in figure 9, 

but this interpretation probably overestimates the 

radius of influence of this pumpage. Between 1968 

and 1970, four public-supply wells were drilled into 

the Lamotte Sandstone beneath the mined areas in the 

cities of Leadwood (Leadwood No. 1 and No. 2), 

Gumbo (Gumbo well), and Park Hills (Park Hills Desloge well, hereinafter referred to as the Desloge well). 

The static water levels in the Leadwood No. 1 and No. 

2 wells (wells 15 and 74, table 5 and fig. 10) and 

Gumbo well (well 80, table 5 and fig. 10) at the time of 

drilling were between an altitude of 393 and 414 ft. 

The Desloge well (well 31, table 5 and fig. 10) is 

located immediately outside the mined areas and the 

altitude of water at the time of drilling (altitude 700 ft) 

was much higher than those altitudes in the Leadwood 

and Gumbo wells. After the mine pumps were shut off 

in 1972, the water level in the Leadwood and Gumbo 

wells has increased more than 200 ft, whereas the 

water level in the Desloge well has increased only 3 ft, 

indicating the effect of dewatering the mines was 

restricted to a relatively small distance from the mine 

cavities.

By 1976 water-level measurements in 13 mine 

shafts made by the St. Joseph Lead Company indicated that water levels in mines south of the Big River 

were identical (Ron Warren, written commun., 1993). 

The identical water levels in these mines reflect the 

fact that all the mines south of the Big River were connected. Water levels in the mines generally stabilized 

in 1979.

Regional ground-water flow in the lower part of 

the St. Francois aquifer generally is toward the north 

with the Big River as the primary ground-water drain 

(fig. 10). The predominant recharge areas are to the 

south and southwest where the Precambrian rocks and 

Lamotte Sandstone are exposed and to the east where 

the Bonneterre Formations crops out extensively (fig. 

7). Ground-water flow in the region is complicated by: 

the absence of the St. Francois confining unit throughout much of the region, the different hydrologic properties of the Bonneterre Formation and Lamotte 

Sandstone, and the presence of the abandoned mine 

cavities.

On a localized scale the St. Francois aquifer can 

be separated into two distinct units based on the much 

larger hydraulic conductivity of the Lamotte Sandstone as compared to that of the Bonneterre Formation. Where the Lamotte Sandstone is overlain by the 

Bonneterre Formation and younger units, water levels 

in wells completed in the Lamotte Sandstone generally 

are higher than the top of the unit. For example, public-supply wells completed in the Lamotte Sandstone 

in Leadwood, Gumbo, and Desloge have water levels 

more than 300 ft above the top of the unit. Water 

flowed from exploration drill holes completed in the 

Lamotte Sandstone along the lower reaches of the Flat 

River in the late 1800's (Buckley, 1908), indicating the 

Bonneterre Formation is a leaky confining unit to the 

underlying Lamotte Sandstone. Many of these drill 

holes in the Big River and Flat River valleys currently 

(1994) have flowing water. The Bonneterre Formation 

also impedes the upward movement of water in discharge areas along the Big River, where hydraulic 

heads in the Lamotte Sandstone are about 15 ft higher 

than the altitude of the river near the junction of the 

Big and Flat Rivers.

The relatively flat hydraulic gradient within the 

mined area is an effect of the water-filled abandoned 

mine cavities on regional water levels. Wells completed in mine cavities south of the Big River have 

similar water levels regardless of their depth or location. Wells adjacent to mine cavities have water levels 

similar to that of the mines if the altitude of the bottom 

of the well is not substantially above the mines.

Hydrogeology 27
90'22'30"

52-30" ~

3T45'

EXPLANATION

 700 

MINED AREA OF THE OLD LEAD BELT

POTENTIOMETRIC CONTOUR Shows altitude at which water level 

would have stood in tightly cased wells. Contour interval 100 feet. 

Datum is sea level

Figure 9. Pre-1972 potentiometric surface of the St. Francois aquifer in the vicinity of the St. Francois 

County Landfill site, Missouri (modified from Wright and Endicott, 1987).

28 Hydrogeology and Water Quality at the SL Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
Table 5. Well inventory data for selected domestic and public-supply wells in the vicinity of the St. Francois County Landfill site, 

[ATD, at time of drilling; uS/cm, microsiemens per centimeter at 25 degrees Celsius; , no data; Bt, Bonneterre Formation; Lm, Lamotte Sandstone; DD, Derb

P, Potosi Dolomite; >, greater than]

o

<Q

O 

<Q

Well no. 

(fig. 10)

1

6

7

10

122

13

14

15

16

20

24

25

27

28

31

32

33

34

35

36

37

38

39

40

41

42

432

Latitude

374941

374804

374914

374953

374927

375150

375058

375127

375418

375034

375148

375523

375157

375224

375229

375623

375626

375548

375529

375459

375513

375500

375427

375218

375439

375622

375734

Longitude

0903456

0903028

0903245

0903245

0902804

0902550

0902814

0903540

0903254

0903132

0903429

0903256

0903259

0903249

0903115

0903124

0903117

0903554

0903458

0903351

0903224

0903118

0903049

0903453

0902642

0903346

0903407

Date 

drilled

-

--

12-03-87

-

-

1983

05-05-40

08-23-68

-

07-73

07-09-77

--

~

-

-

09-05-80

06-24-69

11-01-89

08-01-90

07-11-92

-

-

--

-

1979

1978

Well depth Casing 

(feet below depth 

land (feet below 

surface) land surface)

-

705 507

287

..

-

300

100

790 605

..

410

780

-

..

765 385

260

566 283

348

>300

310 80

-

_.

320

220

-.

Land 

surface 

(feet)

960

1,030

790

880

970

850

820

865.82

895

762.04

830

800

740

789.4

809.4

730

710

870

820

950

750

780

760

775

860

825

800

Geologic 

unit

Bt-Lm1

Bt-Lm1

Bt

Bt 1

Bt1

Lm

Lm

Lm

Bt

Bt3

Bt3

Bt3

Bt

Bt3

Lm

Bt

Lm1

Lm

Lm

DD-Dv

Lm1

Bt-Lm1

Bt-Lm1

Bt

P1

Bt

Bt-Lm1

Static water 

level ATD 

(feet below Date 

land surface) inventoried

09-16-92

329 09-16-92

09-16-92

09-14-92

09-15-94

09-15-94

25 07-15-92

473 09-14-92

04-20-94

09-15-92

09-14-92

04-20-94

09-16-92

09-14-92

09-15-92

09-15-92

109 09-15-92

09-14-92

09-14-92

09-14-92

09-14-92

09-15-92

09-15-92

09-15-92

09-15-92

09-15-92

09-15-92

09-15-92

09-15-92

W

be

s
Table 5. Well inventory data for selected domestic and public-supply wells in the vicinity of the St. Francois County Landfill site, 

CO

0

3

CO

O 

CO

0)

Q.

|

O

fiL

a

(D

11

§

O 

O

(0

o 

o

3

0) 

Q.

0)

Q.

5"

3_

g

1

i

2

0)

f

i

i

Well no. 

(fig. 10)

44

45 

46 

47

48

49

50

51

52

53

54

55

56

57

58 

59

60

63

65

66

67

682

69

70

71

72

73

74

75

Latitude

375646

375610 

375331 

375356

375301

375246

375210

375134

375110

375029

375010

375327

375245 

375327

375452 

375538

375543

375319

375026

375140 

375011

371413

371522

375225

375115

374947

375114

375151

375117

Longitude

0903524

0903444 

0903206 

0903051

0903021

0903529

0903712

0904001

0903718

0903443

0903414

0902914

0902903 

0902744

0902820 

0902938

0902610

0903007

0902817

0902856 

0902631

0902559

0902717

0902745

0902634

0902806

0902915

0903523

0903507 '

Date 

drilled

~

1972

~

1991

1930

-

-

~

1989

-

1970 

1984

1986

1975

04-23-92

-

1992 

1980

1982

1991

1989

1991

1985

-

01-70

_

Well depth Casing 

(feet below depth 

land (feet below 

surface) land surface)

~

-

220

-

--

-

240 100

..

..

270

266

246

--

225

~

325

102

369

282

348

320

-

750

__

Land 

surface 

(feet)

760

780 

800

745

730

780

760

890

910

840

900

760

785 

870

795 

720

790

710

850

815 

905

950

855

825

917

925

785

805

825

Static water 

level ATD 

Geologic (feet below 

unit land surface)

P-Bt1

Bt 

Bt 

Lm1

Bt-Lm1

Bt

Bt

Unknown

Bt

Bt

Bt

Lm1

Lm1 

Lm1

Lm1 

Lm

Lm

Lm

Lm1

Lm 

Lm1

Lm

Lm

Lm

Lm

Lm

Lm1

Lm 391

Bt3

Date 

inventoried

09-15-92

09-15-92 

09-15-92 

09-16-92

09-16-92

09-16-92

09-16-92

09-16-92

09-16-92

09-17-92

09-17-92

09-14-92

09-14-92 

09-14-92

09-14-92 

09-15-92

09-15-92

09-15-92

09-15-92

09-16-92 

09-16-92

09-16-92

09-16-92

09-16-92

09-16-92

09-16-92

09-17-92

09-14-92

09-14-92

W

(f
Table 5. Well inventory data for selected domestic and public-supply wells in the vicinity of the St. Francois County Landfill site, M

Well no. 

(fig. 10) Latitude

76

77

78

79

80

81

82

83

374953

375547

375150

375109

375151

375107

374924

374929

842 374918

Hydrogeology

85

86

87

88

89

90

91

92

93

94

95

96

97

98

99 

100

l

2 

3 

4

2 374938

2 375018

375019

375144

375131

375101

375155

374831

374946

374925

375443

374950

374834

375447

375504 

375042

Longitude

0903247

0903340

0903300

0903408

0903340

0903228

0903212

0903324

0903527

0903714

0903718

0903302

0903230

0903218

0903151

0903354

0903541

0903426

0902606

0903259

0903246

0903457

0902658

0902716 

0903648

Date 

drilled

-

11-09-89

-

--

12-01-69

12-06-88

-

06-23-92

~

01-23-86

~

-

1978-79

-

06-29-87

--

-

1986

09-92

-

-

~

-

10-11-93 

08-88

Well depth Casing 

(feet below depth 

land (feet below 

surface) land surface)

--

750

415

-

565 400

574 80

-

410 80

102

225 105

-

>400

-

..

285 80

--

164

5500

328

~

615

..

185 80 

950

Land 

surface 

(feet)

900

875

790

840

815

905

820

895

1,010

1,010

950

1,010

850

890

880

815

935

960

960

875

880

950

762

760 

1,020

Static water 

level ATD 

Geologic (feet below Date 

unit land surface) inventoried

Bt-Lm

Lm

Bt

Bt

Lm 406

Lm

Bt3

Bt

P

P

P

Lm

Bt

Bt

Bt1 ' 2

Lm

Bt

Lm

Lm

Bt

Bt

Lm

Bt-Lm1

Bt-Lm1 

Lm 375

09-14-92

09-15-92

09-15-92

09-15-92

09-15-92

09-15-92

09-15-92

09-15-92

09-15-92

09-15-92

09-15-92

09-15-92

09-16-92

09-16-92

09-16-92

09-16-92

09-16-92

09-17-92

09-17-92

11-23-93

11-23-93

11-23-93

12-20-93

12-21-93 

01-06-94

W

(fe

s

Geologic unit information is uncertain. 

Water level in this well was not used to prepare the regional potentiometric surface map (fig. 10). 

Well completed in abandoned mine cavity within the Bonneterre Formation.

Static water level of 106 feet (measured during March 1989 after well was shut down for several weeks for repairs) was used to prepare the regional pot

5 Well depth is approximate.
90*37'30 38'

90'22'30"

52'30"

37'45'

EXPLANATION 0 1 

MINED AREA OF THE OLD LEAD BELT

234 5 KILOMETERS

 725 FOTENTIOMETRIC CONTOUR Shows altitude at which water level would 

have stood in tightly cased wells. Dashed where approximately located. 

Contour interval 25 feet. Datum is sea level

ra DOMESTIC OR PUBLIC-SUPPLY WELL AND NUMBER

Figure 10. Potentiometric surface of the lower part of the St. Francois aquifer (1992-83) in the vicinity 

of the St. Francois County Landfill site, Missouri.

32 Hydrogeology and Water Quality at the St Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
Because the mine cavities extend for several miles, the 

hydraulic head in the mine cavities probably is an 

average of hydraulic heads across the region. In effect, 

as mine cavities filled with water and the water levels 

stabilized, the natural gradient was leveled by averaging the higher hydraulic heads in the south with the 

lower hydraulic heads near the Big River. Hydraulic 

heads in mined areas near the Big River probably are 

higher than they were before mining took place. This 

may explain why the hydraulic heads in mined areas 

near the landfill site are 25 to 35 ft higher than the altitude of the Big River as compared to hydraulic heads 

only about 15 ft higher than the altitude of the Big 

River downstream of the mined areas.

In mined areas near the Big River, hydraulic 

heads in the mine cavities probably are higher than the 

hydraulic heads in the underlying Lamotte Sandstone. 

During March 1989, the water-level altitude in the 

Desloge well (703.4 ft; well 31, fig. 10) was nearly 17 

ft lower than the water-level altitude in the Park Hills 

River Mines well, hereafter referred to as the River 

Mines well (720.29 ft; well 20, fig. 10), indicating the

potential for downward flow of mine water in the 

Lamotte Sandstone. The 1989 water level in the Desloge well was used in preparation of the potentiometric surface map because the well had been inactive for 

several weeks before this measurement (Ron Warren, 

written commun., 1994). In localized areas, such as 

the city of Leadwood, water levels in the mines and 

Lamotte Sandstone were nearly identical, indicating 

hydraulic connection between the abandoned mines 

and the Lamotte Sandstone. The water-level altitude in 

the Leadwood No. 1 well (well 15, table 5) was 0.32 ft 

and 0.57 ft below the water-level altitude of the River 

Mines well (well 20, table 5) in September 1992 and 

April 1994.

Water levels in the mine cavities exhibit seasonal variation, decreasing in the summer and increasing in the fall and winter (fig. 11). This variation is 

probably caused by increased recharge during wet seasons. Pumpage from domestic and public-supply wells 

is unlikely to be large enough to affect water levels in 

the mine cavities.

730

720

710

700

690

WATER LEVEL MEASURED IN THE PARK HILLS 

RIVER MINES WELL Data supplied by 

Ron Warren, Park Hills Water Department jt.

. (637.2) x 

/ ^635.4)

 (632.3) 

... I ... I ... I

1976 1977 1978 1979 1980 1981 1982 1983 1984 1985 1986 1987 1988 1989 1990 1991 1992 1993

Rgure 11. Seasonal variation of mine water levels in the vicinity of the St. Francois County Landfill site, Missouri.

Hydrogeology 33
Hydrogeology of the St. Francois County 

Landfill Site

The tailings are composed mainly of variable 

quantities of silt-size (11.5-98 percent by weight) and 

sand-size material (0.8-87.5 percent by weight) with 

small (2 percent or less by weight) quantities of claysize material (table 6). In contrast, a sample of the 

overburden (organic-rich top soil and gravelly clay) 

beneath the tailings (MW-100, 69.5-71.5 ft) contained more than 14 percent by weight clay-size material and only about 10 percent sand-size material. The 

organic carbon contents of the tailings and overburden 

were small, averaging less than 0.2 percent by weight. 

Analyses of three tailings samples indicated they are 

comprised mainly of dolomite with associated ankerite 

(more than 70 percent by weight), quartz (9-12 percent by weight), calcite (4-7 percent by weight), and 

smaller quantities of feldspar and mica and trace quantities of sulfide minerals, such as pyrite. Chemical 

analyses of the coarse (greater than 0.063 mm) and 

fine (less than 0.063 mm) fractions of the tailings indicate both fractions are chemically similar except for 

concentrations of several trace elements. Concentrations of trace elements in both fractions generally were 

less than 100 mg/kg (milligrams per kilogram) except 

for concentrations of Fe (3.2-4.1 percent by weight), 

Pb (910-3,400 mg/kg), Mn (3,700-5,100 mg/kg), and 

Zn (190-1,900 mg/kg). The sample of the overburden 

beneath the tailings contained the largest concentrations of barium (Ba; 460 and 490 mg/kg) and chromium (Cr; 78 and 68 mg/kg) hi the coarse and fine 

fractions and among the smallest concentrations of Pb 

(49 and 51 mg/kg), Mn (1,600 and 1,000 mg/kg), and 

Zn (73 and 76 mg/kg).

Ground-water flow at the landfill site is affected 

by the altitude of the original land surface beneath the 

tailings, the difference between the hydraulic conductivity of the tailings and bedrock, the presence of solution enlarged fractures and joints in the bedrock, the 

location of exploration drill holes beneath the tailings 

pile and landfill, and the proximity of the site to the 

Big River. Water-level measurements indicate a 

ground-water mound in the tailings and shallow bedrock beneath the landfill site. The mound forms a shallow ground-water divide that trends generally 

eastward from the middle of the site (fig. 12). Ground 

water hi the northeastern part of the site flows north 

toward the Big River, and ground water in the southeastern part flows toward Mine-A-Joe Creek. Flow in 

the western one-half of the site generally is toward the

southwest or west toward the Big River. The diversion 

tunnel in the southwest corner of the site may be a 

dram and limit the movement of shallow ground water 

from the landfill site to the southwest.

The nose of the ground-water mound coincides 

with part of the buried Mine-A-Joe Creek valley 

beneath the tailings (fig. 13). The original land surface 

of the buried valley generally slopes northward toward 

the Big River, where the tailings are more than 100 ft 

thick. The original land surface closely approximates 

the top of bedrock as drill logs indicated usually less 

than 1 or 2 ft of overburden between the tailings and 

the bedrock. More than 50 ft of saturated tailings exist 

within the buried creek valley, and the base of the 

landfill is within 15 ft of the potentiometric surface 

(fig. 14). The thickness of saturated tailings decreases 

where the altitude of the original land surface 

increases, and tailings along the east and west boundaries of the site generally are unsaturated (fig. 14). 

Four of the original monitoring wells (MW-102, 

MW-103, MW-104, and MW-105) installed in 1987 

probably intersected perched water because these 

wells have subsequently gone dry. Bedrock piezometers installed near the perimeter of the site (201-P, 

204-P, 205-P, 2020-P, 2021-P, and 2022-P) did not 

encounter appreciable quantities of water above the 

bedrock; however, minor quantities of perched water 

were encountered during the installation of piezometers 204-P and 205-P.

The hydraulic conductivity values determined 

from slug tests hi tailings monitoring wells MW-100 

and MW-101 were 6.1 x 10'6 and 5.4 x 10'6 ft/s. These 

values are somewhat larger than the range of laboratory derived values (2.5 x 10'9 to 2.5 x 10'7 ft/s) 

reported by Gastreich (1974). A probable explanation 

for the differences is that the slug tests evaluated a 

mixture of the silt- and fine sand-size layers under natural densities, conditions difficult to replicate in the 

laboratory. Slug tests in bedrock piezometers 204-P, 

2020-P, 2022-P, and 2023-P indicate the hydraulic 

conductivity of the bedrock (1.0 x 10'7 to 5.0 x 10'6 

ft/s) tends to be slightly smaller than the hydraulic 

conductivity of the tailings. Because of the layered 

nature of the tailings, the slope of the original buried 

land surface, and the slightly smaller hydraulic conductivity of the bedrock as compared to that of the tailings, recharge in the northeastern part of the landfill 

site probably moves downward through the refuse and 

tailings to the ground-water surface, then down the 

buried Mine-A-Joe Creek valley toward the Big River.

34 Hydrogeology and Water Quality at the SL Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
Table 6. Grain size, bulk mineralogy, and selected chemical composition of tailings and overburden samples, St. Francois Count

[All concentrations in percent by weight unless noted otherwise; , not detected; t, trace; <, less than; coarse, greater than 0.063 millimeter; fine, less than 0.063 

Well

(fig- 5)

MW-100

(overburden)

MW-107

108-P

Well

(fig- 5)

MW-100

(overburden)

MW-107 

X 

'£ 108-P

|

1

Depth 

(feet below 

land surface)

9.5-11.5

19.5-21.5

29.5-31.5

39.5-41.5

49.5-51.5

69.5-71.5

55.0-60.0

19.5-21.5

29.5-31.5

39.5-40.5

49.5-51.5

Depth 

(feet below - 

land surface)

9.5-11.5

19.5-21.5

29.5-31.5

39.5-41.5

49.5-51.5

69.5-71.5

55.0-60.0 

19.5-21.5 

29.5-31.5

39.5-40.5 

49.5-51.5

Grain size

Sand

58.2

81.5

57.2

22.2

57.5

10.2

87.5

22.8

41.1

.8

50.5

Calcium

Coarse

21

22

21

20

21

.5

21 

20 

19

21 

21

Silt

40.8

17.6

41.8

76.8

40.5

75.6

11.5

75.9

57.7

98.0

48.7

Clay

1.0

.9

1.0

1.0

2.0

14.2

1.0

1.3

1.2

1.2

.8

Total

11.8

11.9

11.4

10.7

11.7

.32

11.7

11.0

10.1

11.2

11.5

Carbon

Organic

0.20

.10

.10

<.l

.10

.20

.20

.20

.17

<.l

.30

Magnesium

Fine

19

19

18

18

19

.5

18 

18 

19

17 

18

Coarse

11

11

11

10

11

.58

8.3 

10 

9

9.3 

10

Fine

10

11

10

10

9.4

.62

9.9 

10 

10

9.2 

9.1

Coarse

3.5

3.4

4.0

3.6

4.0

4.0

3.4 

3.5 

3.4

3.5 

3.2

Bulk 

Carbonate

11.6

11.8

11.3

10.9

11.6

.12

11.5

10.8

9.93

11.3

11.2

Iron

Fine

3.4

3.5

4.1

3.7

4.0

4.0

3.7 

3.5 

3.5

3.4 

3.3

Dolomite and 

ankerite Quartz

-

78 9

-

-

-

--

78 9

--

-

-

73 12

Arsenic 

(mg/kg)

Coarse Fine

<10 10

<10 10

<10 13

<10 11

<10 <10

14 15

<10 13 

<10 10 

10 10

<10 13

Calcite

~

7

-

--

-

~

7

~

-

~

4

Coarse

47

39

61

80

39

460

38 

79 

110

64 

56

CO

01
Table 6. Grain size, bulk mineralogy, and selected chemical composition of tailings and overburden samples, St. Francois County 

a.

3

(O

o 

o.

o

(Q

0)

3

a.

s0)

0

O

9L

f

j

0

0)

r*

 n

§

i

w 

Oo

c

3

§

a.

0)

a.

Chromium

Depth

Ufall /foot HA|/%UI wen |ieei DGIOW 

(fig. 5) land surface)

MW-100 9.5-11.5

19.5-21.5

29.5-31.5

39.5-41.5

49.5-51.5

(oveiburden) 69.5-71.5

MW-107 55.0-60.0

108-P 19.5-21.5

29.5-31.5

39.5-40.5

49.5-51.5

(mg/kg)

Coarse

6

5

8

10

5

78

5

10

16

8

8

Fine

9

9

11

12

8

68

13

11

11

17

13

Cobalt

(mg/kg)

Coarse

31

29

46

30

22

18

28

23

22

26

39

Fine

44

49

70

33

27

18

53

24

30

23

50

Copper

(mg/kg)

Coarse

31

32

240

49

13

26

6

7

7

6

34

Fine

42

47

340

55

17

25

15

7

8

8

57

Lead

(mg/kg)

Coarse

1,400

910

1,900

1,700

980

49

1,100

1,800

3,000

1,300

1,200

Fine

2,200

1,900

3,400

2,000

1,500

51

2,900

2,100

1,700

3,100

2,000

M

Coarse

4,700

4,500

4,800

4,400

5,100

1,600

4,800

4,500

4,200

4,500

4,100
90*33' 32'50" 32'40" 90*32'30"

37'52'45" -

52'35" -

37*52'25" -

100 200 300 METERS

720

EXPLANATION

APPROXIMATE BOUNDARY OF THE OLD DESLOGE 

CITY DUMP

POTENTIOMETRIC CONTOUR Shows altitude at which 

water level would have stood in tightly cased wells. 

Dashed where approximately located. Contour interval 

10 feet. Datum is sea level

DOMESTIC OR MONITORING WELL OR PIEZOMETER

Figure 12. Potentiometric surface in the tailings and shallow bedrock at the St. Francois County Landfill site, 

Missouri, in November 1993.

Hydrogeology 37
90*33' 32'50" 32'40" 90*32'30"

52'35"

37'52'25"

DEMOLITION

FILL ~-^\ '

\\

APPROXIMATE AREA

OF OLD DESLOGE

CITY DUMP

300

I

600

I

900 FEET

100

I I 

200 300 METERS

EXPLANATION

 720 LINE OF EQUAL ALTITUDE OF ORIGINAL LAND 

SURFACE Contour interval 10 feet

A A' TRACE OF GEOHYDROLOGIC SECTION

 DOMESTIC OR MONITORING WELL OR PIEZOMETER

Figure 13. Altitude of original land surface beneath the St. Francois County Landfill site, Missouri.

38 Hydrogeology and Water Quality at the St. Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
750 1,000 1.250 1,500 1,750 2,000 2,250 2,500

500 750 1,000 1,250 

DISTANCE, IN FEET

1,500 1,750

EXPLANATION

POTENTIOMETRIC 

SURFACE

WELL

OPEN INTERVAL OR 

FILTER PACK

Figure 14. Hydrogeologic sections at the St. Francois County Landfill site, Missouri.

Hydrogeology 39
Although most recharge at the landfill is expected to 

move through the tailings down the buried Mine-AJoe Creek valley, some recharge moves vertically 

through the tailings into the shallow bedrock. Except 

for measurements made on September 9,1993, the 

water-level altitude in tailings piezometer 108-P was 

between 0.14 and 2.43 ft higher than the altitude of 

water in bedrock piezometer 208-P, indicating a 

downward gradient between the tailings and bedrock 

in the vicinity of these wells. Because of the proximity 

of the site to the Big River and a regional groundwater drain, recharge entering the shallow bedrock 

from the tailings will travel along relatively shallow 

flow paths and discharge into the Big River.

The presence of solution-enlarged fractures and 

joints within the bedrock and numerous exploration 

drill holes beneath the tailings pile create the potential 

for some recharge from the tailings pile to move 

deeper into the bedrock and possibly into the abandoned mines. A number of mines in the Old Lead Belt 

received substantial surface inflow through fractures 

and solution channels (Buckley, 1908). Three incidents of tailings ponds partially or completely draining 

into the underlying mines through such channels were 

reported (Buckley, 1908). Two such incidents 

occurred when water in the National Lead Company's 

mill pond drained through a bedrock channel into the 

National No. 2 mine located about 2 mi southeast of 

the landfill site. Surface water carrying debris and several hundred cubic yards of chat entered the Desloge 

No. 3 mine (beneath the Desloge tailings pile and 

landfill site) through fractures and solution channels 

intersecting Mine-A-Joe Creek. Buckley (1908) 

reported these channels were grouted at the surface; a 

reconnaissance of Mine-A-Joe Creek upstream of the 

landfill site failed to locate these grouted channels, 

indicating they may be buried beneath the tailings pile 

and landfill. More than 1,200 exploration drill holes 

are beneath the landfill site 247 lie beneath the sanitary landfill and demolition fill (fig. 15). Most of these 

drill holes were installed in the 1950's after most of 

the Desloge tailings pile was in place. Many of the 

drill holes probably are completed in the abandoned 

mine cavities and possibly in the underlying Lamotte 

Sandstone. Several severely corroded iron pipes 

thought to be surface casing remnants from these drill 

holes were exposed during excavation activities at the 

landfill; however, attempts to obtain water-level measurements in these pipes were unsuccessful because

they were bent or plugged several feet below the land 

surface.

Hydraulic properties of the tailings can be used 

to estimate the time required for landfill contaminants 

to travel from the most recently disposed refuse (about 

300 ft north of piezometer 108-P) downgradient to 

monitoring well MW-106. The macroscopic linear 

velocity is calculated using hydraulic conductivity, the 

slope of the potentiometric surface, and a representative value of tailings porosity. The tailings are primarily silt-size, for which porosity typically ranges from 

35 to 50 percent (Fetter, 1988), averaging 42.5 percent. The hydraulic conductivity values determined 

from slug tests in wells completed in the tailings are 

6.1 x 10'6 ft/s (monitoring well MW-100) and 5.4 x 

10'6 ft/s (monitoring well MW-101). The total distance from the area north of piezometer 108-P to monitoring well MW-106 is about 1,050 ft over which the 

altitude of the potentiometric surface decreases 70 ft, 

indicating an average hydraulic gradient of -0.067. 

Based on the two values of hydraulic conductivity, the 

time required for leachate to travel from this area of 

landfill to monitoring well MW-106 could be between 

35 and 40 years. Using the same technique and 

hydraulic conductivity values, it would take between 

10 and 12 years for leachate to travel from a deep hole 

filled with refuse near piezometer 2021-P to monitoring well MW-106. The tailings were emplaced in layers and range in composition from silt- to sand-size 

particles. Because of the complexities of the media 

and because only two slug tests were performed in 

wells completed in the tailings, travel time calculations can only give a general indication of the actual 

time required for leachate to travel to monitoring well 

MW-106. Estimating travel time to piezometers completed in bedrock is equivocal, because of flow from 

tailings into bedrock and multiple flow paths (exploration drill holes, fractures, and bedding planes) within 

the Bonneterre Formation.

WATER QUALITY

Ground- and surface-water quality in the region 

varies due to the presence of varied lithology types 

and the presence of sulfide mineralization. Human 

activities, such as mining, agriculture, industry, and 

refuse disposal, also may affect water quality.

40 Hydrogeology and Water Quality at the St. Francois County Landfiii and Vicinity, Southeastern Missouri 1990-84
 I

90'33' 32'50" 32'40" 90*32*30"

37'52'45"

52'35'

37'52'25" -

Mined area and drill hole locations supplied by the Missouri Division 

of Geology and Land Suiwy 300i

600i900 FEET

100 200 300 METERS

EXPLANATION 

MINED AREA 

EXPLORATION DRILL HOLE

APPROXIMATE BOUNDARY OF THE 

OLD DESLODGE CITY DUMP

Rgure 15. Extent of underground mine workings and location of abandoned exploration drill holes beneath the 

St. Francois County Landfill site, Missouri.

Water Quality 41
Regional Ground-Water Quality

The quality of water in wells completed in the 

St. Francois aquifer is related to the location of the 

well, proximity to mineralized areas, and whether the 

well is completed in the Lamotte Sandstone, Bonneterre Formation, or abandoned mine cavities. The 

specific conductance of water samples from wells 

completed primarily in the Lamotte Sandstone (35 

wells inventoried) ranged from 413 to 735 [iS/cm 

(mean of 566 [iS/cm), except for samples from the two 

public-supply wells in the city of Leadwood where the 

specific conductance values were greater than 1,000 

uS/cm. The specific conductance of water samples 

from wells probably completed only in the Bonneterre 

Formation (21 wells inventoried) ranged from 712 to 

1,593 u\S/cm (mean of 1,017 u\S/cm). The specific 

conductance of water samples from wells known to be 

completed in the abandoned mine cavities (4 wells 

inventoried) ranged from 930 to 1,415 pS/cm (mean 

of 1,160 uJS/cm). Specific conductance values larger 

than about 1,000 pS/cm in the St. Francois aquifer 

probably indicate effects from naturally occurring sulfide mineralization or the influx of high specific conductance water from the abandoned mine cavities.

The range of selected physical properties and 

concentrations of chemical constituents in the St. 

Francois aquifer in the region is given in table 7. Values in table 7 are derived from 47 water-quality samples collected from 17 public-supply wells between 

1988 and 1991 (Linda Killian, Missouri Department 

of Natural Resources, Public Drinking Water Program, 

written commun., 1994). Most of the wells obtain 

water from the Lamotte Sandstone; however, a few 

wells are completed in the Bonneterre Formation or 

abandoned mine cavities. The distribution of major 

ions reflects the dissolution of carbonate material 

within the aquifer. Water in the wells ranges from a 

Ca-Magnesium (Mg)-HCO3 to a Mg-HCO3 type, with 

water from the Bonneterre Formation generally harder 

than water from the Lamotte Sandstone. Water from 

the abandoned mine cavities ranges from a Ca-MgHCO3 to a Ca-Mg-SO4-HC03 water. Concentrations 

of dissolved Na in the St. Francois aquifer generally 

are less than about 10 mg/L, but concentrations in 

excess of 30 mg/L have been reported in areas northwest of the Old Lead Belt where the water type can be 

Na-HCO3 (Imes andDavis, 1991). Concentrations of 

SO4 in the aquifer outside of the mined areas usually 

are less than 150 mg/L. Concentrations of SO4 larger 

than 250 mg/L are associated with mineralized areas,

such as in the vicinity of the abandoned mine cavities 

or near Precambrian basement rock exposures along 

the Simms Mountain Fault System. Concentrations of 

dissolved trace elements, except for copper (Cu), Fe, 

Mn, and Zn, were less than the detection level (table 

7).

The USEPA sampled 42 domestic wells in the 

vicinity of the Desloge tailings pile (including the 

landfill well) for physical properties, dissolved major 

constituents, and dissolved and total trace elements 

(Ecology and Environment, 1992). The formations 

these wells are completed in were not furnished; however, specific conductance values ranged from 370 to 

1,300 pS/cm, indicating that the wells were completed 

in the Lamotte Sandstone, the abandoned mines, or 

mineralized parts of the Lamotte Sandstone or Bonneterre Formation. Concentrations of Ca and Mg in 

samples from these wells ranged from 42.1 and 19 

mg/L to more than 140 mg/L, and concentrations of 

Na ranged from 2.2 to 45.5 mg/L. Concentrations of 

trace elements generally were small. Four wells contained detectable concentrations of Pbt (5.9-33 pg/L), 

and two wells contained detectable concentrations of 

dissolved Pb (6.6 and 26 pg/L). Concentrations of 

total Zn (Znt) ranged from less than 20 to 467 pg/L, 

and concentrations of dissolved Zn ranged from less 

than 20 to 463 |ig/L.

Background Ground-Water Quality at the 

Landfill Site and Vicinity

Water samples were collected from monitoring 

well MW-100, piezometers 201-P and 2022-P (figs. 2 

and 5), and the Baker Mine well (well 24, fig. 10) to 

evaluate background water quality and geochemical 

conditions in the tailings, shallow bedrock, and mine 

cavities. Analytical data for the flowing drill hole west 

of the landfill site (Smith and Schumacher, 1991) were 

also used to characterize background conditions in the 

mine cavities. In addition, samples were collected 

from public-supply wells in Desloge, Gumbo, and 

Leadwood. Usage of the term background refers to 

ambient water quality and geochemical conditions 

existing in the respective media in areas not affected 

by the landfill. Monitoring well MW-100 is located 

about 2,500 ft north of a east-west trending groundwater trough located between monitoring well MW101 and piezometer 2020-P. The selection of piezometers 201-P and 2022-P as background monitoring points is somewhat equivocal because ground

42 Hydrogeology and Water Quality at the St Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
Table 7. Range of selected physical properties and chemical constituents in samples from selected public-supply wells 

completed in the St. Francois aquifer, Missouri

[Data are summarized from the results of water-quality samples collected between 1988 and 1991 by the Missouri Department of Natural Resources, 

Public Drinking Water Program (Linda Killian, Missouri Department of Natural Resources, Public Drinking Water Program, written commun., 1994); 

<, less than]

Physical property or constituent

pH, in standard units

Calcium, in milligrams per liter

Magnesium, in milligrams per liter

Sodium, in milligrams per liter

Potassium, in milligrams per liter

Minimum

7.3

34

35

2.5

.8

Maximum

7.9

163

105

30

4.3

Mean

7.5

82

53

9.2

2.0

Hardness, in milligrams per liter as CaCO3 

Sulfate, in milligrams per liter 

Chloride, in milligrams per liter 

Fluoride, in milligrams per liter 

Bicarbonate, in milligrams per liter

236

11

2

294

.1

840

531

20

1

420

421

154

8.8

.4

347

Total dissolved solids, in milligrams per liter 

Nitrite plus nitrate as nitrogen, in milligrams per liter 

Arsenic, in micrograms per liter 

Barium, in micrograms per liter 

Cadmium, in micrograms per liter

Chromium, in micrograms per liter 

Copper, in micrograms per liter 

Iron, in micrograms per liter 

Lead, in micrograms per liter 

Manganese, in micrograms per liter

Mercury, in micrograms per liter 

Selenium, in micrograms per liter 

Silver, in micrograms per liter 

Zinc, in micrograms per liter

258 

<.05 

<5

<200 

<5

<25

<100

<20

<5 

<100

1,128 

3.36

<5 

<200

<5

<25

50

480

50

<5

500

532

1.00 

<5

<200 

<5

<25

<210

<33

<5 

<5

<210

water from the southern part of the landfill flows to the 

south (fig. 12). However, ground water from the southeast part of the landfill flows to the west of piezometer 

201-P, and shallow ground water from the southwest 

part of the landfill probably flows toward the west or 

southwest to the Big River or is intercepted by the 

diversion tunnel. Piezometers 201-P and 2022-P did 

not contain increased concentrations of constituents 

commonly associated with landfill leachate (table 4) 

during sampling in 1993. The Baker Mine well (well 

24, fig. 10) is located several miles southwest of the 

landfill site and probably upgradient of the landfill in

the regional flow system. The flowing drill hole west 

of the landfill site also lies somewhat upgradient of the 

landfill in the regional flow system.

Physical Properties and Inorganic Constituents

Ground-water samples from the background 

sites in the tailings, shallow bedrock, and mine cavities in the vicinity of the landfill site had specific conductivity values ranging from 921 to 1,500 pS/cm; 

near neutral pH values; and Ca, Mg, SO4, and HCO3 

as the predominant ions (table 8). These samples plot

Water Quality 43
o

<Q

O 

<Q

B)

Q.

B)

O

B)

ABBREVIATIONS AND REPORTING UNITS FOR CHEMICAL CONSTITUENT

AND NOTATIONS USED IN TABLE 8

CO

o

SC

pH 

DO 

COD 

Ca

Mg

Mgt

Na

K

 n

3

§

o>

O 

o

c

1-

B)

3 

Q.

=j

B)

3

Q.

HCO3(rT)

S04

Cl

F

TDS

Hard

TOC

NO2+NO3t

NH3t

^

cu

OUj

As 

Ast 

Ba

B

Bt 

Cd

Cd,

Specific conductance, in microsiemens per centimeter

at 25 degrees Celsius 

In standard units

Dissolved oxygen, in milligrams per liter 

Chemical oxygen demand, in milligrams per liter 

Calcium, dissolved, in milligrams per liter 

Calcium, total, in milligrams per liter 

Magnesium, dissolved, in milligrams per liter 

Magnesium, total, in milligrams per liter 

Sodium, dissolved, in milligrams per liter 

Sodium, total, in milligrams per liter 

Potassium, dissolved, in milligrams per liter 

Alkalinity, total, in milligrams per liter as CaCO3 ,

by incremental titration

Bicarbonate, in milligrams per liter, by incremental titration 

Sulfate, dissolved, in milligrams per liter 

Chloride, dissolved, in milligrams per liter 

Fluoride, dissolved, in milligrams per liter 

Dissolved solids, sum of constituents, in milligrams per liter 

Hardness, total, in milligrams per liter as CaCO3 

Organic carbon, total, in milligrams per liter 

Nitrite plus nitrate, total as nitrogen, in milligrams per liter 

Ammonia, total as nitrogen, in milligrams per liter 

Phosphorous, total, in milligrams per liter 

Antimony, total, in micrograms per liter 

Arsenic, dissolved, in micrograms per liter 

Arsenic, total, in micrograms per liter 

Barium, dissolved, in micrograms per liter 

Barium, total, in micrograms per liter 

Boron, dissolved, in micrograms per liter 

Boron, total, in micrograms per liter 

Cadmium, dissolved, in micrograms per liter 

Cadmium, total, in micrograms per liter

Cr Chromium, dissolved, in microg

Crt Chromium, total, in micrograms 

Co Cobalt, dissolved, in microgram

Cot Cobalt, total, in micrograms per 

Cu Copper, dissolved, in microgram

Cut Copper, total, in micrograms per 

Fe Iron, dissolved, in micrograms p

Fet Iron, total, in micrograms per lit

Pb Lead, dissolved, in micrograms 

Pbt Lead, total, in micrograms per li

Li Lithium, dissolved, in microgram

Mn Manganese, dissolved, in microg

Mnt Manganese, total, in microgram

Hg Mercury, dissolved, in microgra

Hgt Mercury, total, in micrograms p

Mo Molybdenum, dissolved, in micr

Ni Nickel, dissolved, in microgram

Nit Nickel, total, in micrograms per 

Se Selenium, dissolved, in microgr

Set Selenium, total, in micrograms p

Ag Silver, dissolved, in micrograms 

Agt Silver, total, in micrograms per 

Sr Strontium, dissolved, in microgr

Tl Thallium, dissolved, in microgra

V Vanadium, dissolved, in microg

Vt Vanadium, total, in micrograms 

Zn Zinc, dissolved, in micrograms p

Znt Zinc, total, in micrograms per li

< Less than 

	No data
Table 8. Range of selected physical properties and chemical constituents from background sites in the tailings, 

shallow bedrock, and mine cavities in the vicinity of the St. Francois County Landfill site, Missouri

Physical property 

or chemical 

constituent

SC

PH

DO

COD

Ca

Cat

Mg

Mgt

Na

Nat

K

Alk(IT)

HCO3(IT)

SO4

Cl

F

TDS

Hard

TOC

NO2+NO3t

NH3t

Pt

Sbt

As

Ast

Ba

Bat

B

Bt

Cd

Cdt

Cr

Crt

Co

Cot

Cu

Cut

Fe

Fet

Tailings 

(MW-100) 

(fig. 5)

1,110-1,340

7.5-7.7

<.5

<10-26

71-95

85-189

110-120

120-150

5.9-9.4

3.1-9.2

11-11.9

288-303

328-370

450-500

2.3-3.3

.5-.6

808-887

630-1,090

.9-14.8

<.02-.28

.43-.S2

<.02-1.2

<1-1

-

11-30

41-55

50

562-610

560-640

<1

<l-7

<5

<5-ll

<3

<3-43

<10

<10-34

41-250

530-28,900

Shallow bedrock 

(201-P, 2022-P)

(fig. 5)

955-1,500

6.9-7.3

<.5

<10

100-180

180-200

72-110

100-120

10-14

13-15

.73-2.5

238-414

290-505

240-520

6.2-9.7

<.l

645-1,090

550-900

.8-6.5

<.02-.19

<.01-.09

<.02-.06

<l-4

-

2-4

20-39

20-80

30-230

210-230

<1

<l-6

<5

<5

3-30

20

<10

<10-15

14-160

310-4,900

Mine cavity 

(Baker Mine well and drill hole) 

(figs. 5 and 10)

921-1,220

6.2-7.5

<.5

<10-18

110-130

120-130

58-74

63-73

6.1-11

8.4-8.8

2.7-5.1

258-516

314-630

250-420

9.3-14

<.l-.2

622-902

520-630

.6-1.9

<.02-.71

.01-.04

.01 -.03

<1

<1

<l-3

20-28

20-30

60-90

<230

<l-2

<1

<5

<5

<3-30

6-10

<10

<10-11

<3-2,400

2,000-3,000

Water Quality 45
Table 8. Range of selected physical properties and chemical constituents from background sites in the tailings, 

shallow bedrock, and mine cavities in the vicinity of the St. Francois County Landfill site, Missouri Continued

Physical property 

or chemical 

constituent

Pb

Pbt

Li

Mn

Mnt

Hg

Hgt

Mo

Ni

Nit

Se

Set

Ag

Agt

Sr

Tl

V

vt

Zn

Znt

Tailings 

(MW-100) 

(fig. 5)

<10

28-2,360

24-29

240-270

290-3,620

-

<.2

<10-20

<10

<10

<1

<5

<l-2

<5

290-360

<1

<6

<l-3

<4-8

7-424

Shallow bedrock 

(201-P, 2022-P)

(fig. 5)

<10-50

110-1,200

<4-10

21-720

690-1,200

--

<1

<10

10-20

20-30

<1

<1

<1

<1

110-130

<1

<6

<6

10-140

110-240

Mine cavity 

(Baker Mine well and drill hole) 

(figs. 5 and 10)

<10-30

5-21

4-17

17-160

52-73

<.l

<1

<10

10-80

10-30

<1

<1

<1

<1

94-120

<1

<6

<6

22-310

90-220

within a narrow band on a trilinear diagram between 

the Ca plus Mg-CO3 vertex and the Ca plus Mg-SO4 

plus Cl vertex (fig. 16).

Concentrations of COD (less than 10-26 mg/L), 

Na (5.9-14 mg/L), Cl (2.3-14 mg/L), NO2+NO3t (less 

than 0.02-0.71 mg/L), and NH3t (less than 0.01-0.52 

mg/L) were relatively small in samples from the background sites. Concentrations of SO4 (240-520 mg/L) 

and Fe (less than 3-2,400 |ig/L) were, however, moderately large.

Concentrations of Ca (170-180 mg/L), Mg (93- 

110 mg/L), SO4 (480-520 mg/L), and several trace 

elements in samples from piezometer 201-P (table 9, 

at the back of this report) generally were larger than 

concentrations in samples from public-supply wells in 

the region (table 7) and the Baker Mine well (table 9). 

The large concentrations of various constituents in 

samples from piezometer 201-P are attributed to naturally occurring sulfide mineralization in the bedrock in 

this area. Abundant pyrite and marcasite (FeS2) and 

galena (PbS) were observed in drill cuttings during the 

installation of this piezometer. A sample from piezometer 2022-P, located in a relatively non-mineralized part of the bedrock, had smaller concentrations of 

Ca (100 mg/L), Mg (72 mg/L), and SO4 (240 mg/L) 

than those in samples from piezometer 201-P, and the 

concentrations were comparable to those detected in 

samples from public-supply wells (table 7).

Except for boron (B), total boron (Bt), Fe, Fet, 

Pbt, Mn, Mnt, strontium (Sr), Zn, and Znt, concentrations of most trace elements ranged from less than the 

detection level to a few tens of micrograms per liter. 

Ground-water samples from the tailings tended to 

have the largest concentrations of total trace elements, 

whereas samples from the mines and bedrock tended 

to have the largest concentrations of dissolved trace 

elements (table 8). Samples from the tailings, however, tended to have larger concentrations of Sr in 

addition to large concentrations of total arsenic (Ast), 

Ba, B, Bt, and lithium (Li). The large concentrations of 

B and Bt are anomalous, because B-rich minerals have 

not been identified in the tailings or sedimentary rocks 

in the region. Appreciable quantities of B are contained within P ore and phosphate (PO4) reagents,

46 Hydrogeology and Water Quality at the St Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
CALCIUM CHLORIDE PLUS NITRATE 

PERCENT OF TOTAL MILLIEQUIVALENTS PER LITER

EXPLANATION

BACKGROUND SITES 

(MW-100, 201-P, 

2022-P, BAKER MINE 

WELL, DRILL HOLE)

MW-101

MW-103

MW-105

MW-106

MW-107

108-P

MW-109

A 204-P

+ 205-P

X 208-P

O 2020-P

V 2021-P

B 2023-P

X MW-303

* LANDFILL WELL

® DOMESTIC WELL

Rgure 16. Trilinear diagram of major constituents in ground-water samples from the St. Francois 

County Landfill site and vicinity, Missouri.

Water Quality 47
such as detergents. A potential source of B could be 

reagents used in the milling process. Taggart (1945) 

indicated that PO4 was used in the flotation process to 

precipitate Ca, Mg, and trace elements and to depress 

the formation of non-silicate salts of these ions.

Molar ratios of Ca to Mg in the tailings are 

small (0.39-0.48; table 10) as compared to a nearly 

1:1 ratio in the bedrock (0.84-1.11) and mines (1.03- 

1.26). The molar ratios of Ca to Mg indicate the predominant source of Ca and Mg in water from the tailings, bedrock, and mine cavities is dissolution of 

dolomite [(Ca, Mg)(CO3)2]. The small molar ratio of 

Ca to Mg in the tailings indicates the dissolution of 

dolomite and subsequent precipitation of nearly pure 

calcite.

Mineral saturation indices (SI) calculated using 

the computer code WATEQ4F (Ball and others, 1987)

indicate probable solubility controls on aqueous concentrations of several major ions (Ca, Mg, and HCO3). 

A thorough discussion of this concept is given in Ball 

and others (1987). A SI of zero indicates the solution 

is at equilibrium with a given mineral phase; values 

larger than zero indicate super saturation, and values 

less than zero indicate the solution is undersaturated 

with a given mineral phase. An error of ± 0.5 in the SI 

often is used for common minerals phases, such as calcite (CaCO3), whereas errors for most trace element 

mineral phases (such as galena) may be much larger. 

Aqueous concentrations of Ca and HCO3 in the tailings, bedrock, and mines probably are controlled by 

the dissolution of dolomite or calcite and precipitation 

of aragonite, a metastable form of calcite. Aqueous 

concentrations of Mg in the tailings may be controlled 

by the precipitation of magnesite (MgCO3) because

Table 10. Molar ratios of calcium to magnesium and saturation indices for selected mineral phases in water samples from 

background sites in the vicinity of the St. Francois County Landfill site, Missouri

[Ca, calcium; Mg, magnesium; , no data]

Well 

(figs. 5 and 10)

MW- 100 (tailings)

201-P (bedrock)

2020-P (bedrock)

Baker Mine well (mine)

Drill hole (mine)

Date

03-30-93

06-22-93

!09-28-93

10-27-93

03-29-93

06-22-93

!09-28-93

10-27-93

12-21-93

04-25-90

04-01-93

06-24-93

!09-29-93

10-29-93

02-24-88

05-17-88

09-27-88

11-30-88

03-02-89

05-04-89

09-14-89

Ca/Mg 

ratio

0.42

.39

.48

.44

1.07

.99

1.11

1.09

.84

1.07

1.14

1.14

1.26

1.14

1.14

1.12

1.04

1.03

1.08

1.09

1.11

Saturation Index

Aragonite

0.11

.08

.01

.14

.13

.03

-.24

.05

.01

.08

.05

-.19

.12

-.01

-.09

.23

-.03

-.22

-.30

-.20

-1.09

Calcite

0.26

.23

.26

.29

.28

.18

-.08

.20

.16

.23

.21

-.04

.27

.15

.07

.38

.13

-.07

-.15

-.05

-.93

Dolomite

0.82

.80

.75

.87

.48

.30

-.28

.29

.32

.39

.29

-.19

.38

.18

-.02

.65

.17

-.24

-.42

-.22

-1.98

Gypsum

-1.10

-1.11

--

-1.06

-.80

-.77

-

-.78

-1.21

-1.00

-1.03

-.91

--

-.98

-1.10

-1.09

-1.12

-1.13

-1.14

-1.13

-1.14

Magnesite

0.08

.09

.01

.09

-.30

-.36

-.69

-.40

-.32

-.32

-.40

-.64

-.38

-.46

-.57

-.22

-.44

-.66

-.75

-.65

-1.53

1 Sulfate concentrations are not available for this sample, and saturation indices for minerals are estimated.

48 Hydrogeology and Water Quality at the SL Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
the SI values (0.01-0.09) indicate near saturation with 

this mineral phase (table 10). Dolomite is slightly 

supersaturated in the tailings (0.75-0.87) and slightly 

undersaturated or near equilibrium in the bedrock 

(-0.28-0.48) and mine cavities (-1.98-0.65). Reaction 

kinetics of dolomite dissolution are slow, which probably explains the slight supersaturation in the tailings.

The distribution of trace elements in ground 

water at the landfill site reflects their solid-phase abundances in the tailings and bedrock and geochemical 

controls on their solubilities. For example, Fe, Pb, and 

Mn are abundant in the bedrock and tailings; however, 

only Fe and Mn were detected in substantial quantities 

in ground-water samples from these media. Concentrations of Pb probably are limited by the formation of 

Pb-oxides, Pb-carbonate (cerussite), and sorption onto 

clay minerals (Smith and Schumacher, 1991). Iron, Pb, 

and Zn are mainly derived from sulfide minerals, such 

as FeS2, PbS, and sphalerite (ZnS). The predominant 

sources of Li, Mn, and Sr are carbonate minerals (calcite and dolomite) within the tailings and bedrock.

Pesticides and Volatile Organic Compounds

Background concentrations of pesticides and 

VOC were determined in samples from monitoring 

well MW-100, piezometer 201-P, piezometer 2022-P 

(VOC only), the Baker Mine well, and the River

Mines well (wells 20 and 24, fig. 10). The flowing drill 

hole west of the landfill site was not accessible during 

the time samples for background pesticide and VOC 

concentrations were collected. The Leadwood wells 

No. 1 and No. 2 (wells 15 and 74, fig. 10), the Gumbo 

well (well 80, fig. 10), and the Desloge well (well 31, 

fig. 10) also were sampled to provide additional background concentrations of VOC in the Lamotte Sandstone beneath mined (Leadwood wells) and unmined 

(Gumbo and Desloge wells) areas. A VOC sample 

also was collected from the Elvins tailings pile seep, 

previously sampled (Smith and Schumacher, 1991), to 

provide an additional tailings background sample. All 

pesticide and VOC samples were analyzed for the 

entire list of compounds in table 2.

Diazinon, a commonly used lawn and garden 

insecticide, was detected in several background sites 

in the tailings, bedrock, and mine cavities. Diazinon 

was detected at 17 ng/L (nanograms per liter) in the 

sample from monitoring well MW-100 and at 4 ng/L 

in piezometer 201-P (table 11). The presence of diazinon in monitoring well MW-100 cannot be attributed 

to documented usage around the tailings ponds. Diazinon in the sample from monitoring well MW-100 

could be derived from runoff from an old brush and 

yard waste disposal area 600 ft west of this well. The 

source of the small (4 ng/L) concentration of diazinon

Table 11. Concentrations of pesticides detected in water samples from monitoring and public-supply wells in the vicinity of the 

St. Francois County Landfill site, Missouri

[ng/L, nanograms per liter; <, less than; , no data]

Well 

(figs. Sand 10)

MW-100

MW-106

MW-107

108-P

MW-109

201-P

204-P

205-P

208-P

MW-303

Landfill well

Baker Mine well

Park Hills River Mines well

Date

09-28-93

09-29-93

09-29-93

09-28-93

09-29-93

09-28-93

09-28-93

09-28-93

09-28-93

09-28-93

11-24-93

09-29-93

11-24-93

Time

1335

0900

0930

1735

1030

1030'

1500

1600

1840

0825

0915

1330

1612

Diazinon, 

dissolved 

(ng/L)

17

<8

24

11

<8

4

3

<8

2

6

<8

<8

<8

Prometon, 

dissolved 

(ng/L)

<8

<8

<8

<8

<8

<8

<8

<8

<8

57

65

8

17

Terbacil, water 

filtered 

(ng/L)

<30

<30

<30

54

<30

<30

<30

<30

<30

<30

<30

<30

<30

Total pesticides 

detected 

(ng/L)

17

-

24

65

~

4

3

-

2

63

65

8

17

Water Quality 49
in piezometer 201-P could be the landfill or nonpoint 

sources from residential areas less than 0.5 mi to the 

east.

Prometon (the active ingredient in the nonselective herbicide Pramitrol) was detected at 8 ng/L in the 

sample from the Baker Mine well and at 17 ng/L in the 

sample from the River Mines well. The occurrence of 

prometon in both the Baker Mine well and River 

Mines well (more than 3 mi apart) may indicate the 

presence of widespread low-level contamination of the 

mine cavities. Extensive use of prometon has not been 

documented in the region; however, the occurrence 

indicates a nonpoint source or multiple localized 

sources, such as usage around mill buildings during 

operation of the mines.

Small concentrations of benzene (0.2-0.3 jig/L, 

table 12, at the back of this report) were detected in the 

background tailings well (MW-100). No VOC were 

detected in the background bedrock piezometers (201- 

P and 2022-P); however, concentrations of several 

VOC were detected in the mine cavities. Small concentrations of methyltertiarybutylether (MTBE) were 

detected in samples from the Baker Mine well (0.2- 

0.4 ug/L) and in the River Mines well (0.3 jJ,g/L). Concentrations of 1,1,2,2-tetrachloroethene (PCE) at the 

detection level (0.1 jig/L) were detected in samples 

from the Baker Mine well and the River Mines well. 

No VOC were detected in the Leadwood No. 1 well, 

Gumbo well, or Desloge well; however, 0.74 jig/L of 

benzene was detected in the sample from the Leadwood No. 2 well. Benzene commonly is in fuels, such 

as gasoline, many lubricants, hydraulic fluids, and solvents, and is used in the manufacture of a variety of 

chemicals from pharmaceuticals to pesticides. The 

small concentrations of benzene in monitoring well 

MW-100 could be contamination introduced during 

drilling or residual contamination from the use of creosote in the ore flotation process (Taggart, 1945). The 

predominant use of MTBE is as an additive in gasoline 

and other fuels. Because of its nonflammability, PCE 

is a commonly used industrial solvent. The most likely 

source of the small concentrations of PCE and MTBE 

in the mine cavities is old unsalvageable equipment 

and supplies left underground when the mines were 

closed. Equipment used in the mines was electric 

(such as locomotives) or air powered (such as the 

shovel used to load shot rock into ore cars) and was 

serviced in underground maintenance shops. The 

source of benzene in the Leadwood No. 2 well could

be related to mining activities or other sources near the 

wellhead.

Distribution of Contaminants in Ground Water

The physical properties and chemical constituents judged to be the best indicators of landfill leachate 

effects at the landfill site were specific conductance, 

Ca, Na, Alk(IT), Cl, NH3t, Ba, Fe, pesticides other than 

prometon, and VOC other than MTBE and carbon disulfide (CS2). Although large Ca concentrations are not 

unique to landfill leachate, anomalously large Ca values may indicate the dissolution of carbonate minerals 

within the tailings during the neutralization of organic 

acids present in landfill leachate. Anomalously large 

concentrations of Alk(IT) also may indicate the presence of landfill leachate. Large concentrations of 

Alk(IT) can be the result of: (1) analytical errors in the 

titration method caused by the presence of organic 

acid anions such as acetate (C2H3O21 ') or oxygen-containing organic compounds that are weak bases; (2) 

additional HCO3 present from the neutralization of 

acidic leachate by carbonate minerals; and (3) additional HCO3 present from the bacterial production of 

CO2 gas and subsequent formation of carbonic acid 

and HCO3 . Large concentrations of Na, Cl, and NH3t 

typically characterize landfill leachate, and the small 

background concentrations of these constituents 

makes them useful tracers of leachate effects from the 

landfill.

The large concentrations of trace elements commonly reported in landfill leachate predominantly are 

derived from refuse within the landfill. Leachate generated within the St. Francois County Landfill, however, may also contain SO4 and trace elements derived 

from the dissolution of ore minerals within the tailings. Minerals such as PbS, ZnS, chalcopyrite 

(CuFeS2), sieginite [(Co,Ni)3S4], FeS2, andbravoite 

[(Ni,Fe)S2] present in the Old Lead Belt (Snyder and 

Gerdemann, 1968) can contain abundant quantities of 

a variety of trace elements, including cadmium (Cd), 

cobalt (Co), Cr, Cu, Fe, Pb, nickel (Ni), and Zn. 

Increased concentrations of SO4 and these elements 

have been detected in seeps emerging from tailings 

piles in the region (Smith and Schumacher, 1991). The 

presence of naturally occurring trace elements in 

ground water from the tailings, bedrock, and mine 

cavities in the region makes an identification of landfill leachate based solely on SO4 and trace element distributions equivocal. Concentrations of Ba, however,

50 Hydrogeology and Water Quality at the St Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
in the water samples from background sites generally 

were small (55 (ig/L or less). In addition, concentrations of Fe in water samples from the background tailings and bedrock sites (MW-100,201-P, and 2022-P) 

were small (less than 250 (ig/L) as compared to concentrations commonly detected (0.2-5,500 ug/L) in 

landfill leachate (table 4). Background concentrations 

of Fe in the mine cavities, however, were much larger 

(as much as 2,400 ug/L) than concentrations from 

background tailings and bedrock sites.

Small concentrations of the pesticide prometon 

and the VOC MTBE were detected in samples from 

the background mine cavity site (Baker Mine well, 

tables 11 and 12) and in samples from several publicsupply wells in the region. The occurrence of these 

two compounds in the mine-cavity system makes their 

use as indicators of landfill leachate equivocal. A common degradation product of the xanthates used in the 

ore processing is CS2, limiting its usefulness as an 

indicator of landfill leachate.

To determine if the water quality of samples 

from monitoring wells, piezometers, and seeps at the 

landfill site was affected by the landfill, values of 

physical properties and concentrations of chemical 

constituents in samples from various sites at the landfill were compared to background concentrations 

reported in the previous section (table 8). Data from 

tailings monitoring wells, piezometer 108-P, and 

seeps G, H, and K were compared to background values represented by data from monitoring well MW100. Data from piezometers, wells, and seeps in the 

bedrock (seep 10+07) were compared to background 

values represented by data from piezometers 201-P 

and 2022-P. Water-quality data from monitoring 

points in the mine cavities were compared to background values characteristic of the mine cavities represented by data from the Baker Mine well and the drill 

hole west of the landfill site.

Physical Properties and Major Inorganic 

Constituents

Sample results from monitoring wells MW106, MW-107, and MW-109 and piezometers 108-P, 

208-P, 2021-P, and 2023-P, and the domestic well 

south of the landfill site (fig. 2) plot outside the range 

for background sites on a trilinear diagram (fig. 16). 

Water in these wells and piezometers tends to be a CaMg-HCO3 type, compared to the mixed Ca-Mg-SO4- 

HCO3 type typical of ground water in the tailings, 

bedrock, and mine cavities in the region. Values of

specific conductance and various physical properties 

and concentrations of major constituents in samples 

from these sites commonly exceeded the background 

values determined for the tailings or bedrock.

The largest constituent concentrations were 

detected in samples from tailings monitoring wells 

MW-106, MW-107, and MW-109 and piezometer 

108-P. Samples from monitoring well MW-303 and 

piezometer 208-P contained generally the largest concentrations of major constituents in samples from bedrock and mine cavity monitoring points, and samples 

from piezometer 205-P contained among the smallest. 

Concentrations of total major constituents compared 

favorably with dissolved concentrations, with the total 

concentrations usually equal to or slightly larger than 

the dissolved concentrations (table 9).

Specific conductance values in monitoring well 

and piezometer samples collected at the landfill site 

ranged from 473 uS/cm in a sample from monitoring 

well MW-105 to 2,260 uS/cm in samples from monitoring well MW-106 (table 9; values of 330 and 3,000 

uS/cm in samples from monitoring wells MW-106 

and MW-103 were considered suspect). Samples from 

monitoring well MW-106 also contained among the 

largest concentrations of COD (7-150 mg/L), Ca 

(160-356 mg/L), Na (28-96 mg/L), potassium (K; 25- 

39 mg/L), Alk(IT) (840-1,040 mg/L), Cl (44-151 

mg/L), TOC (4.6-71.6 mg/L), NO2+NO3 (less than 

0.05-5.9 mg/L as N), and NH3t (13-28 mg/L as N). 

These concentrations were larger than background 

concentrations for tailings (table 8) in most sampling 

rounds. A strong smell of H2S was detected during the 

sampling of this well. Water-quality samples from 

seep K, located about 25 ft downslope of monitoring 

well MW-106, also contained specific conductance 

values and concentrations of COD, Ca, Na, K, Alk(iT), 

Cl, NH3 , and NH3t larger than background (table 13, 

at the back of this report). The discharge of this seep 

was estimated at less than 0.01 ft3/s. Monitoring well 

MW-106 and seep K are submerged occasionally during high flow on the Big River and constantly are 

being covered by wind-blown tailings and small 

slumps at the base of the pile that may, in part, explain 

the variable water quality observed in MW-106.

Samples from monitoring wells MW-101, 

MW-103, MW-104, MW-107, and MW-109, and 

piezometers 108-P, 204-P, 208-P, 2020-P, 2021-P, 

and 2023-P also had specific conductance values or 

concentrations of COD, Ca, Mg, Na, K, Alk(IT), SO4, 

Cl, NO2+NO3t, NH3t, and TOC larger than backWater Quality 51
ground. Samples from three of these sites (MW-103, 

204-P, and 2020-P), however, plotted within the range 

of background sites on a trilinear diagram (fig. 16), 

indicating the distribution of major constituents in 

these samples was not substantially different from that 

of the background sites. Insufficient data were available to plot samples from monitoring well MW-104. 

None of the samples from bedrock piezometers had 

larger than background specific conductance values or 

concentrations of Ca, Mg, or 804.

Concentrations of Na larger than background 

(9.4 mg/L tailings, 14 mg/L bedrock) also were 

detected in samples from monitoring wells (table 9) 

MW-107 (29-33 mg/L) and MW-109 (28-150 mg/L) 

and piezometers 108-P (63-69 mg/L), 204-P (14-16 

mg/L), 208-P (35-46 mg/L), 2021-P (130 mg/L), and 

2023-P (46 mg/L). Between March and October 1993, 

concentrations of Na in samples from monitoring well 

MW-109 decreased with time (150-28 mg/L), 

whereas concentrations of Ca (110-150 mg/L) and Mg 

(64-73 mg/L) increased. Concentrations of other indicator constituents such as Cl and NH3t had no such 

trends. The molar equivalent decrease in the Na charge 

(about 5 millimoles per liter) was almost balanced by 

the increase in equivalences of Ca plus Mg (about 3 

millimoles per liter), indicating ion exchange may be 

affecting the concentrations of major cations in samples from this well. The most likely cause is the 

exchange of Ca or Mg for Na in the Na-bentonite used 

as the annular seal. Exchange reactions typically occur 

rapidly, and the concentrations of Ca, Mg, and Na stabilized by October 1993.

Larger than background concentrations of 

Alk(IT) (303 mg/L) also were detected in samples from 

tailings monitoring wells MW-101 (321 and 333 

mg/L), MW-103 (346 and 381 mg/L), MW-107 

(582-623 mg/L), and MW-109 (528-676 mg/L), piezometer 108-P (328-349 mg/L), and bedrock piezometer 2021-P (439 mg/L, background bedrock 

concentration of 414 mg/L). Larger than background 

concentrations of Cl (3.3 mg/L tailings, 9.7 mg/L bedrock) were detected in samples from monitoring wells 

MW-101 (less than 1-66 mg/L), MW-103 (less than 

1-46 mg/L), MW-104 (4-64 mg/L), MW-107 (38-51 

mg/L), and MW-109 (32-40 mg/L) and piezometers 

108-P (95-110 mg/L), 204-P (17-20 mg/L), 208-P 

(44_45 mg/L), 2021-P (44 mg/L), and 2023-P (78 

mg/L). Concentrations of Cl in samples from piezometer 205-P (7.5-11 mg/L) were only slightly 

above background.

The largest concentrations of NH3 or NH3t in 

the tailings or bedrock (excluding samples from monitoring well MW-106) were detected in samples from 

monitoring wells MW-107 (2.1-3.62 mg/L) and 

MW-109 (2-3.02 mg/L) and piezometers 108-P (2.3- 

4.8 mg/L) and 2023-P (2.5 mg/L; table 9). An NH3 

concentration of 8.5 mg/L in a sample from monitoring well MW-105 (January 18,1988; table 9) was 

more than 10 times larger than any other concentration 

from this well and is suspect.

Several samples from two seeps (seep G and H) 

emerging from the base of the tailings and a bedding 

plane in the bedrock near monitoring well MW-104 

had specific conductance values or concentrations of 

COD, Ca, Na, K, Alk(IT), SO4, and Cl (table 13) larger 

than background for tailings. Seep G is the seep near 

the drainage tower that was sampled by the Missouri 

DGLS and Missouri DEQ in 1980 and 1988. Between 

1980 and 1989, specific conductance values and concentrations of most constituents in samples from this 

seep increased. However, except for slightly increased 

concentrations of Ca (96 and 99 mg/L, background of 

95 mg/L) and Cl (3.5 and 3.6 mg/L, background of 3.3 

mg/L), concentrations of major constituents in samples from seep G decreased to less than background in 

samples collected on June 7,1990. Specific conductance values and concentrations of most major constituents in two samples from seep H (about 25 ft east of 

seep G) collected in April and June 1990 were larger 

than concentrations in samples from seep G. Both 

seeps have been dry between mid-1991 and the 

present (1994).

A number of bedding plane seeps were observed 

during a reconnaissance of the diversion tunnel in 

April 1990. Small seeps (flowing less than 25 mL per 

minute) were observed along a pronounced bedding 

plane along the entire 1,500 ft length of the tunnel. 

Between the tunnel entrance and the bend that underlies the landfill office, seep orifices on the north side of 

the tunnel tended to be encrusted with orange and 

black Fe and Mn oxy-hydroxides. Seep orifices on the 

south side of the tunnel along this same reach were 

clear and had no Fe or Mn staining. Seep 10+07, the 

largest of the Fe-stained seeps, is about 150 ft past the 

bend on the north side of the tunnel. Concentrations of 

Na, K, Cl, NO2+NO3t, and NH3t in samples from this 

seep have increased to larger than background bedrock 

concentrations since the initial sampling in June 1990. 

Concentrations of Na and NH3 or NH3t increased an 

order of magnitude from 2.9 and 0.36 mg/L to 30 and

52 Hydrogeology and Water Quality at the St Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
4.8 mg/L; concentrations of K doubled (4.1-8.5 

mg/L), and concentrations of Cl increased from 6.1 to 

44 mg/L.

Trace Elements

The potential for landfill leachate to mobilize 

large quantities of trace elements from the tailings was 

evaluated through a series of laboratory leaching 

experiments. Fine (less than 0.063 mm) and coarse 

(greater than 0.063 mm) tailings from the landfill site 

were leached under batch conditions with leachate 

obtained from a leachate collection system at a municipal sanitary landfill in Topeka, Kansas. Leachate from 

the St. Francois County Landfill was not used because 

of the difficulty in obtaining leachate that had not contacted tailings. Experiments were carried out under 

oxygen-rich and oxygen-poor conditions over 5 days. 

Concentrations of dissolved trace elements in the initial leachate were Cd (less than 3 Mg/L), Cr (less than 5 

Mg/L), Co (14 Mg/L), Cu (less than 10 Mg/L), Pb (56 

Mg/L), and Zn (48 Mg/L). A detailed description of the 

experimental conditions and analytical results is given 

byDixon(1994).

The results of die laboratory experiments indicate that landfill leachate can mobilize measurable 

quantities of trace elements from the mine tailings at 

the landfill site. Under near-neutral pH conditions, 

experimental results indicated variable increases in the 

dissolved concentrations of Co (271-957 percent), Cu 

(0-2,350 percent), Pb (0-650 percent), and Zn (608- 

1,168 percent). The coarse tailings contributed the 

largest concentrations of Co, Cu, and Zn to the 

leachate solution (maximum solution concentrations 

of 169, 336, and 620 Mg/L), whereas the fine tailings 

contributed the largest concentrations of Pb (maximum solution concentration of 939 Mg/L). Concentrations of Cd and Cr did not increase substantially in the 

experiments. In anoxic experiments, solution concentrations of Cu and Pb actually decreased, indicating 

possible precipitation of reduced phases. The landfill 

leachate extracted 5 times more Pb and 30 times more 

Zn than similar experiments using rainwater (Dixon, 

1994). Based on the laboratory experiments, leachate 

generated at the St. Francois County Landfill may contain increased concentrations of Co, Cu, Pb, and Zn 

derived from interaction of organic acids with mineral 

phases in the tailings.

Samples from several monitoring wells, piezometers, and seeps in the tailings and bedrock contained detectable concentrations of trace elements

indicative of landfill leachate (Ba and Fe) and several 

trace elements (Co, Cu, Pb, and Zn) mobilized in the 

laboratory experiments (tables 9 and 13). Concentrations of most trace elements in samples from the landfill site generally were smaller than those detected in 

the laboratory experiments, indicating that dilution or 

geochemical reactions may restrict trace element 

mobility as leachate mixes with ambient ground water 

and migrates farther from the landfill. Concentrations 

of most other trace elements, except arsenic (As), Ast, 

Ni, total nickel (Nit), and Sr, were small and near the 

background concentrations for the various media 

(table 8). Occasional outliers in the results indicate 

possible laboratory error, sampling error, or heterogeneity in the solid-phase composition of the tailings and 

bedrock. Total concentrations of most trace elements, 

especially Fet, Pbt, Mnt, and Znt, in several samples 

from tailings monitoring points were much larger than 

dissolved concentrations, which indicates small quantities of aquifer particulates were disturbed during 

sampling. Because of this potential problem, dissolved 

concentrations of trace elements generally were used 

to interpret water quality and identify contaminant 

migration from the landfill.

Concentrations of trace elements were largest in 

samples from tailings monitoring wells and piezometers. Samples from monitoring well MW-106 (table 

9), in addition to having among the largest concentrations of major constituents, also contained among the 

largest concentrations of As (4-49 Mg/L), Ba (80-371 

Mg/L), Cu (6-27 Mg/L), Fe (9-29,100 Mg/L), Pb (less 

than 10-68 Mg/L), Ni (less than 30-50 Mg/L), and Zn 

(5-1,300 Mg/L) larger than background concentrations for tailings. Concentrations of Ast larger than the 

background tailings concentration of 30 Mg/L (table 8) 

were detected in one or more samples from monitoring 

wells MW-107 (26-41 Mg/L; table 9), MW-109 (21- 

41 Mg/L), and piezometer 108-P (13-35 Mg/L). Concentrations of Ast in samples from piezometers 204-P 

(less than 1-7 Mg/L) and 208-P (less than 1-5 Mg/L) 

were only slightly larger than the background bedrock 

concentration of 4 Mg/L (table 8). No Ast data were 

available for piezometers 2020-P, 2021-P, 2022-P, or 

2023-P.

Concentrations of Ba exceeded the background 

tailings concentration of 55 Mg/L (table 8) in one or 

more samples from monitoring wells MW-101, MW103, MW-105, MW-106, and MW-107, piezometer 

108-P, and seeps G and K. Excluding samples from 

monitoring well MW-106, the largest Ba concentraWater Quality 53
tions were detected in samples from seep K (130-240 

ug/L; table 13) and monitoring wells MW-101 (19- 

180 ug/L; table 9) and MW-107 (110-120 ug/L). 

Concentrations of Ba larger than the background bedrock concentration of 39 ug/L (table 8) were detected 

in bedrock piezometers 204-P (26-46 ug/L), 208-P 

(29-55 ug/L), 2020-P (56 ug/L), 2021-P (100 ug/L), 

and 2023-P (81 ug/L) and the domestic well (58 ug/L; 

table 9). Concentrations of Ba in monitoring well 

MW-303 (25-30 ug/L; table 9) were only slightly 

larger than the background mine cavity concentration 

of 28 ug/L (table 8) and are within analytical error.

Samples from monitoring wells MW-101, 

MW-103, MW-106, MW-107, and MW-109, piezometers 108-P and 2020-P, and seeps G and K contained Fe concentrations larger than the background 

concentration for the various media. Excluding samples from monitoring well MW-106, the largest Fe 

concentrations detected were in samples from monitoring wells MW-103 (40-8,900 ug/L) and MW-107 

(1,400-2,500 ug/L) and seep K (7-6,100 ug/L). By 

comparison the largest Fe concentration detected in 

the bedrock was 330 ug/L in a sample from piezometer 2020-P (table 9).

Larger than background concentrations of Pb, 

Ni, and Zn were detected in samples from monitoring 

wells MW-103, MW-105, MW-106, MW-107, and 

MW-109 and seeps G and H. The largest concentrations of Pb tended to be in samples from seeps G (less 

than 10-80 ug/L) and H (20 and 170 ug/L). Concentrations in the tailings monitoring wells generally were 

less than 50 ug/L except in several samples collected 

during early 1989 from MW-101 (72 ug/L), MW-103 

(88 ug/L), MW-106 (68 ug/L), and one sample collected in June 1990 from MW-105 (70 ug/L). A Pb 

concentration of 420 ug/L in a sample from MW-106 

(May 1992; table 9) is suspect. One sample from monitoring well MW-303 contained a Pb concentration of 

40 ug/L (table 9) slightly larger than the background 

concentration of 30 ug/L for mine cavities (table 8). 

Concentrations of Ni in the tailings monitoring wells 

generally were less than 50 ug/L except in one sample 

from monitoring well MW-103 (70 ug/L).

Samples from all tailings monitoring wells and 

seeps G, H, and K contained concentrations of Co and 

Zn larger than those detected in the background tailings well (MW-100; table 8). Concentrations of Co 

(less than 3 ug/L) and Zn (less than 3-8 Ug/L) 

detected in samples from monitoring well MW-100 

probably are not representative of the background

variability within the tailings. The distribution of Coand Zn-rich minerals in the ore bodies within the Old 

Lead Belt was erratic consequently the distribution 

of these minerals within the tailings piles is erratic. 

The small Co and Zn concentrations in samples from 

monitoring well MW-100 probably indicate that the 

tailings in the vicinity of this well were derived from 

Co- and Zn-poor host rock. The concentrations of Co 

and Zn detected in tailings samples from the landfill 

site generally were less than the concentrations of Co 

(310-610 ug/L) and Zn (11,000-18,000 ug/L) 

detected in samples from the Elvins tailings pile seep 

(table 13) and probably within the range of background concentrations in mine tailings.

Pesticides and Volatile Organic Compounds

Monitoring wells MW-100, MW-106, MW107, MW-109, and MW-303, piezometers 108-P, 

204-P, 205-P, and 208-P, the landfill well, Baker 

Mine well, and River Mines well were sampled once 

between September and November 1993 for 47 

selected pesticides (table 2). Samples for VOC determinations were collected quarterly between March 

and November 1993 from the above sites (excluding 

the River Mines well). Synoptic samples were collected from piezometer 2022-P, seep 10+07, the 

domestic well south of the landfill site, the Elvins tailings pile seep, public-supply wells in the cities of 

Leadwood (Leadwood No. 1 and No. 2), Gumbo 

(Gumbo well), and Park Hills (Desloge well and River 

Mines well), and the Big River upstream (Big River at 

Bone-hole) and downstream (Big River downstream) 

of the landfill site (table 12). The VOC samples were 

analyzed for the constituents listed in table 2. A graphical representation of the distribution of pesticides and 

VOC in well samples collected in October 1993 from 

the landfill site and vicinity is given in figure 17.

Concentrations of diazinon were detected in 

samples from monitoring wells MW-107 (24 ng/L; 

table 11) and MW-303 (6 ng/L) and piezometers 

108-P (11 ng/L), 204-P (3 ng/L), and 208-P (2 ng/L). 

In addition to diazinon, the sample from piezometer 

108-P contained a large concentration of the selective 

herbicide terbacil (54 ng/L). Terbacil is a relatively 

uncommon herbicide and is used on fruit crops, such 

as apples, peaches, and blueberries, and on alfalfa. The 

detection of the nonselective herbicide prometon was 

confined to monitoring points in the abandoned mines. 

Concentrations of prometon in samples from monitoring well MW-303 (57 ng/L) and the landfill well (65

54 Hydrogeology and Water Quality at the St Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
O

o>

70

60

40

30

20

10

Diazinon 17

Benzene 0.3 

Toluene 0.1

H^t 

CH2CIF 

CHCLF

VC

cis-DCE

trans-DCE

Benzene

MTBE

2.3

19*

23* 

0.4 

0.2* 

1.6 

1.8 

0.6 

0.3* 

4.7 

0.2* 

0.14 

4.6

Ethyl ether 97

Diazinon 24

CH.CI 0.2* 

CH2CI, 5.9 

CH.CIF 13* 

Benzene 0.13 

MTBE 0.7 

Ethyl ether 9.5

Diazinon 11 

Terbacil 54

CH2CL

CH2CIF

CHC^F

CS.

cis-DCE

Benzene

MTBE

9.3

5.5*

2.7*

1.8

0.2

0.2

0.4

EXPLANATION

The solid bar represents the total amount of pe

detected in nanograms per liter. The shaded 

represents the total amount of volatile organic 

detected in micrograms per liter

CH,CI Chloromethane

CH2CI2 Dichloromethane

CH2CIF Chlorofluoromethane

CHCUF Djchlorofluoromethane

CCI2F2 Dichlorodifluoromethane

CCI3F Trichlorofluoromethane

CS, Carbon disulfide

C2H5CI Chloroethane

DCA 1,1-Dichloroethane

TCA 1,1,1-Trichloroethane

VC Vinyl chloride

1,1-DCE 1,1-Dichloroethene

cis-DCE tis-1,2-Dichloroethene

trans-DCE trans-1,2-Dichloroethene

TCE 1,1,2-Trichloroethene

PCE 1,1,2,2-Tetrachloroethene

E-benzene Ethylbenzene

MTBE Methyftertiarybutylether

Ethyl ether 10

Not detected in this sample, 

but maximum concentration 

detected in other samples 

from this site

CH2CI, 0.4* 

Benzene 0.5 

MTBE 0.1

.Diazinon 4 .Diazinon

3 CS, 0.4

Diazinon 2 

E-benzene 0.2* 

Xytenes 0.5* 

Napttiatene 0.6*

Prome

I 

PCE 

MTBE 

Q_

SCM

u_

§

Rgure 17. Total mass of pesticides and volatile organic compounds detected in ground-water samples collected in 

Landfill site, Missouri.
ng/L) were larger than the concentrations detected in 

the background mine sites at the Baker Mine well (8 

ng/L) and River Mines well (17 ng/L).

Samples from monitoring wells MW-106, 

MW-107, MW-109, and MW-303, piezometers 108- 

P, 205-P, and 208-P, and the landfill well contained 

detectable concentrations of VOC (table 12). More 

than 20 VOC were detected in ground-water samples 

from the landfill site, with the largest frequency of 

detections and concentrations in samples from monitoring wells MW-106, MW-107, and MW-109. Samples from monitoring well MW-106 contained 

detectable concentrations of dichloromethane (0.3-2.3 

Mg/L), chlorofluoromethane (less than 0.2-38 Mg/L), 

dichlorofluoromethane (less than 0.2-23 Mg/L), 

dichlorodifluoromethane (less than 0.2-0.4 Mg/L), 

trichlorofluoromethane (less than or equal to 0.2 

Mg/L), CS2 (less than 0.2-1.6 Mg/L), chloroethane 

(0.2-1.8 Mg/L), 1,1-dichloroethane (DCA; 0.6-1 

Mg/L), vinyl chloride (VC; less than 0.2-0.3 Mg/L), 

cis-l,2-dichloroethene (cis-DCE; 4.7-16 Mg/L), trans1,2-dichloroethene (trans-DCE; less than or equal 0.2 

Mg/L), benzene (0.14-0.2 Mg/L), MTBE (2-4.6 Mg/L), 

and ethyl ether (18-97 Mg/L).

Concentrations of dichloromethane in samples 

from monitoring wells MW-107 (5.4-11 Mg/L) and 

MW-109 (9-11 Mg/L) and CS2 (1.8 Mg/L) in the October 1993 sample from monitoring well MW-109 were 

the largest concentrations detected. Samples from 

these monitoring wells also contained detectable concentrations of chlorofluoromethane, dichlorofluoromethane, benzene, MTBE, and ethyl ether. 

Monitoring wells MW-106, MW-107, and MW-109 

are located immediately north of an older (about 1973 

to 1980) part of the sanitary landfill. According to the 

landfill operator, wastes from a shoe manufacturing 

plant were placed in this area during the early years of 

landfill operation, and the probable source of the 

VOC detected in these three monitoring wells are solvents and other materials contained in these wastes.

The only VOC detected in samples from piezometer 205-P was CS2 (0.4 Mg/L). The small concentrations (less than 1 Mg/L) of ethylbenzene, 

xylenes, napthalene, and several nontarget VOC 

detected in the March 1993 sample from piezometer 

208-P may be the result of down-hole contamination 

from a hydraulic line break during piezometer installation.

Samples from the landfill well contained trichlorofluoromethane (0.3 Mg/L in one sample), 1,1,1-

trichloroethane (TCA; less than 0.2-0.7 Mg/L), 1,1- 

dichloroethene (1,1-DCE; less than 0.2-0.3 Mg/L), cisDCE (less than 0.2 Mg/L), 1,1,2-trichloroethene (TCE; 

0.2 Mg/L or less), PCE (0.4-0.6 Mg/L), toluene (0.3 

Mg/L in two samples), and MTBE (0.2-0.4 Mg/L). A 

sample collected from this well on January 26,1994, 

was the only sample in which acetone (9.7 Mg/L) and 

2-butanone (6.1 Mg/L) were detected. A probable 

source of these compounds is PVC cements used in 

the installation of a new pump and discharge line several days before the January samples were collected. 

Samples from monitoring well MW-303 contained 

concentrations of cis-DCE (less than or equal to 0.2 

Mg/L), TCE (0.2 Mg/L in the October 1993 sample), 

PCE (0.5-0.6 Mg/L), and MTBE (0.4 Mg/L) similar to 

those detected in samples from the landfill well.

The compound DCA (detected in samples from 

MW-106) commonly is used as a solvent for varnishes and paints and in some ore flotation processes. 

Vinyl chloride is used in the plastics industry and 

occasionally as a refrigerant. In anaerobic environments, such as within a sanitary landfill, cis-DCE and 

VC can be derived from the microbial decomposition 

of TCE. Trans-DCE commonly is used as a solvent for 

fats, phenol, and camphor (Budavari and others, 

1989). Trichlorofluoromethane (Freon 11), dichlorodifluoromethane (Freon 12), and chloroethane commonly are used as refrigerants and aerosol propellants.

Dichloromethane is a common solvent in paint 

removers and degreasing agents. Benzene is widely 

used in the manufacture of a variety of industrial 

chemicals and used as a solvent for paints and varnishes. Benzene also is a component of most fuels 

(such as diesel and gasoline) and lubricating oils. The 

presence of chlorofluoromethane (Freon 31) and 

dichlorofluoromethane (Freon 21) in samples from 

monitoring wells MW-106, MW-107, and MW-109 

is somewhat anomalous because these compounds 

have not been widely used for more than 20 years 

(Angila Menton, Dupont Chemical Corporation, written commun., 1994). Chlorofluoromethane and dichlorofluoromethane may have been used as degreasers. 

Their relatively high boiling points (about -9 and 9 °C) 

would not make them effective refrigerants or aerosol 

propellants. These compounds possibly also may be 

reductive-dechlorination decomposition products of 

more chlorinated molecules such as trichlorofluoromethane or dichlorodifluoromethane. Ethyl ether is 

widely used as a solvent in the manufacture of explo56 Hydrogeology and Water Quality at the St. Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
sives and as a gasoline engine primer (Budavari and 

others, 1989).

Surface-Water Quality

Although surface-water quality was not a major 

focus of this investigation, a limited number of samples were collected from streams in the vicinity of the 

landfill. During October 1993, water-quality samples 

were collected from the Big River at the Bone-hole 

(Big River at Bone-hole; fig. 5) and downstream of the 

landfill about 150 ft downstream of monitoring well 

MW-106 (Big River downstream; fig. 5).

During the October 1993 sample collection, the 

discharge and specific conductance values at the 

upstream site were 119 ft3/s and 510 jxS/cm as compared to 122 ft3/s and 468 jxS/cm measured at the 

downstream site (table 13). Except for a slight 

increase in the concentration of SO4 (49-54 mg/L) and 

NO2+NO3t (0.05-0.09 mg/L) and decrease in the concentration of total phosphorous (Pt; 0.13-0.02 mg/L), 

concentrations of major constituents at the upstream 

and downstream site were similar. Concentrations of 

Fet, Pbt, and Mnt were smaller at the downstream site, 

whereas concentrations of B, Zn, and Znt were larger 

downstream. Small concentrations of xylenes and toluene were detected in samples from the upstream (0.2 

and 0.14 jxg/L) and downstream (0.3 and 0.2 jxg/L) 

sites (table 12). Concentrations of most inorganic constituents in these samples were smaller than concentrations in base flow samples collected on November 7, 

1989 (table 13). The smaller concentrations detected 

in this study probably are the result of dilution by runoff, because the discharges during the 1993 sampling 

were about three times larger than those during the 

1989 sampling.

Samples from Mine-A-Joe Creek downstream 

of the diversion tunnel (tunnel seep; fig. 5) had the 

largest values of specific conductance and concentrations of chemical constituents as compared to samples 

from the Big River and Mine-A-Joe Creek upstream of 

the tunnel (table 13). Although several samples have 

been collected from Mine-A-Joe Creek upstream and 

downstream of the diversion tunnel, the upstream and 

downstream samples were collected by various agencies on different dates using different sample collection and analytical methods and, therefore, are not 

directly comparable. Despite these inconsistencies, the 

concentrations of Co (less than 3-88 jxg/L), Ni (20-60 

|Lig/L), and Zn (72-740 jxg/L) in samples downstream

of the diversion tunnel were larger than the maximum 

concentrations detected in samples upstream of the 

tunnel (Co, less than 3 jxg/L; Ni, less than 10 pg/L; 

and Zn, 9nd 63 jxg/L), suggesting the source of these 

constituents is within the tunnel, probably the numerous small seeps emerging from fractures and bedding 

planes along the tunnel walls.

EFFECTS OF THE LANDFILL ON WATER 

QUALITY

The analytical results of water-quality sampling 

indicate a complex distribution of inorganic and 

organic constituents within the tailings, bedrock, and 

mine cavities at the landfill site and vicinity. Evaluation of the data indicates that ground water at the landfill site has been affected by contaminants originating 

from the landfill and relic contamination from mining 

activities. Because detailed water-quality samples 

have been collected for less than a year at most sites 

and pesticide and VOC data are not available for several of the newer piezometers (2020-P, 2021-P, and 

2023-P), a comprehensive interpretation of how constituent concentrations vary through time is not possible.

Samples from several monitoring wells and piezometers in the tailings and bedrock contained concentrations of inorganic constituents larger than the 

respective background values established for these 

media. A one-way analysis of variance (ANOVA) and 

Tukey's honest significant difference (HSD) multiplecomparison tests (Helsel and Hirsch, 1992) were performed on ranked data from background sites (MW100, 201-P, 2022-P, Baker Mine, and drill hole) and 

monitoring wells and piezometers at the landfill site. 

The ANOVA and HSD tests were used to compare 

water-quality data from monitoring wells and piezometers within each media (tailings, bedrock, and 

mine cavities). Data from piezometer 2022-P were 

grouped with data from piezometer 201-P to represent 

background conditions within the bedrock. Because 

water-quality data tend to be non-normally distributed, 

the data were transformed by a joint ranking procedure. Values flagged as questionable in table 9 were 

not used in the ANOVA and HSD tests. Data from 

monitoring wells MW-103, MW-104, and MW-105 

and piezometers 2020-P, 2021-P, and 2023-P were 

not included in the ANOVA because of insufficient 

sample size.

Effects of the Landfill on Water Quality 57
A students t-test [alpha level (a-level) of 0.05] 

was used to compare physical property and major constituent data collected previously by the landfill to data 

collected during this investigation. Most physical 

property and major constituent data were comparable, 

with the exception of specific conductance, Na, and Cl 

concentrations in samples from monitoring well MW106, which indicated significant differences. Because 

of differences in sampling protocols previously used 

and the methods used in this investigation and known 

sensitivity in trace element data to sampling technique, only trace element data collected during this 

investigation were used in the ANOVA and HSD tests.

An a-level of 0.05 was used for ANOVA procedures, and the null hypothesis, which states that all 

sites within a group (tailings, bedrock, and mine cavities) have equal mean ranks for a given constituent, 

was rejected for analyses with probability values (pvalues) less than 0.05. The a-level is the significance 

level of the test and is established before reviewing the 

data. The p-value is the attained significance level and

is determined by the data (Inman and Conover, 1983). 

The multiple-comparison test was used to determine 

significant differences in values of physical properties 

or constituent concentrations between sites within 

each group. Usage of the Tukey's HSD procedure 

allowed the overall error rate to be controlled at 0.05 

(Snedecor and Cochran, 1980).

The ANOVA indicated significant differences 

between the mean ranks of several constituents in 

samples from monitoring wells and piezometers in the 

tailings, bedrock, and mine cavities. In general, the 

differences were detected between the mean ranks of 

physical properties and constituents determined previously to be indicative of landfill leachate effects (specific conductance, Ca, Na, Alk(IT), Cl, NH3t, Ba, and 

Fe) at tailings and bedrock monitoring points. Few 

significant differences were detected between mean 

ranks of most trace elements, especially total trace elements. An example of the ANOVA and HSD tests is 

graphically summarized in figure 18, and the results 

are in figures 19, 20, and 21.

EXPLANATION

MEAN CONSTITUENT RANK

NV NO VARIANCE

Shaded boxes graphically summarize the results of a one-way analysis of variance (ANOVA) and all possible 

pairwise multiple-comparison tests. Shaded boxes in each column represent the relative mean constituent rank 

for each site. The absence of a shaded box in a column indicates that insufficient data were available for 

analysis. Sites with boxes shaded in the lowermost rows have among the smallest mean constituent ranks. Those 

sites with boxes shaded in the uppermost rows have among the largest mean constituent ranks. Two or more 

sites with boxes shaded in the same row indicate their respective mean constituent ranks are not significantly 

different at an alpha level of 0.05. Two shaded boxes in the same column indicate that the mean constituent rank 

of the site is not significantly different at an alpha level of 0.05 from mean ranks of two or more sites that have 

shaded boxes in the same rows. However, the mean constituent ranks of the other sites that are not in the same 

row are significantly different.

For example, monitoring well MW-100 

and piezometer 108-P have boxes shaded in 

the lowermost row indicating that their mean 

constituent ranks are among the smallest 

detected in the tailings. The boxes for these 

two sites are shaded on the same row 

indicating that their mean ranks of dissolved 

calcium are not significantly different at an 

ajpha level of 0.05. The mean ranks of 

dissolved calcium in samples from MW-107 

and MW-109 also were not significantly 

different; however, their mean ranks were 

significantly larger than those of samples 

from monitoring well MW-100 and piezometer 

108-P. Mean ranks of dissolved calcium In 

samples from monitoring well MW-101 and 

MW-106 were not significantly different; 

however, mean ranks of dissolved calcium in 

samples from these two wells were 

significantly larger than those from the other 

tailings sites.

Rgure 18. Example of results from analysis of variance and multiple-comparison tests.

MW-100 MW-101 MW-106 MW-107 108-P MW-109

58 Hydrogeology and Water Quality at the St Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
MW-100 MW-101 MW-106 MW-107 108-P MW-109 MW-100 MW-101 MW-106 MW-107 108-P MW-109

Rgure 19. Results of analysis of variance and multiple-comparison tests on ranked data for selected physical 

properties and chemical constituents from tailings monitoring wells and piezometers at the St. Francois County 

Landfill site, Missouri.

Effects of the Landfill on Water Quality 59
201-P 

2022-P

204-P 205-P 208-P 201-P 

2022-P

204-P 205-P 208-P

Rgune 20. Results of analysis of variance and multiple-comparison tests on ranked data for selected physical 

properties and chemical constituents from bedrock piezometers at the St. Francois County Landfill site, Missouri.

60 Hydrogeology and Water Quality at the St. Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
DISSOLVED BARIUM DISSOLVED CHLORIDE TOTAL SODIUM 

m

!

5?

Q.

I 

o

0)

3 o>

-«.

s.

3

81

3s

.

OD CD

as3

D 

tO

CO O

"

DISSOLVED IRON TOTAL AMMONIA TOTAL ALKALINITY, PH 4.5 
Tailings

The water quality near monitoring wells (MW106, MW-107, and MW-109) and seep K has been 

affected by the landfill. These wells and seep K are 

downgradient from most of the sanitary landfill, near 

the lower end of the buried creek valley (fig. 13). The 

detection of landfill contaminants in this area indicates 

leachate from the landfill is migrating down the buried 

creek valley toward the Big River. A predominant 

pathway for leachate migration is through the tailings 

down this buried creek valley. Mean ranks of specific 

conductance, Ca, Na, Alk(jT), Cl, NH3t, Ba, and Fe in 

samples from monitoring well MW-106 were significantly larger than those in the background tailings well 

(MW-100) and among the largest detected in the tailings (fig. 19). Except for specific conductance and Ba, 

the mean ranks of these constituents in samples from 

monitoring wells MW-107 and MW-109 also were 

significantly larger than background mean ranks for 

the tailings. Concentrations of trace elements in samples from monitoring wells MW-107 and MW-109 

were much smaller than the maximum concentrations 

detected in the laboratory leaching experiments. If 

leachate from the St. Francois County Landfill is 

mobilizing trace elements from the tailings, the 

smaller trace element concentrations detected in 

ground-water samples may be related to dilution of 

landfill leachate, sorption, or re-precipitation of trace 

elements as they migrate farther from the landfill. In 

addition to the significantly larger concentrations of 

indicator constituents, samples from monitoring wells 

MW-106, MW-107, and MW-109 contained the largest concentrations of diazinon (24 ng/L in the sample 

from MW-107) and VOC detected at the landfill site 

and vicinity.

The water quality in tailings near the center of 

the site also has been affected by the migration of 

leachate from the landfill as evidenced by the large 

concentrations of indicator constituents and pesticides 

in samples from piezometer 108-P. Mean ranks of Na, 

Alk(IT), Cl, and NH3t in samples from this piezometer 

were significantly larger than background (fig. 19) and 

indicate the presence of landfill leachate. Although 

VOC concentrations were small (0.5 jig/L) in samples 

from this piezometer (possibly because it is adjacent to 

the most recent fill), concentrations of pesticides 

(diazinon, 11 ng/L; terbacil, 54 ng/L) were large. A 

sample from this piezometer contained a tritium concentration of 16.0 pCi/L (picocuries per liter; table 9),

indicating a measurable component of post-1952 

water in this well.

Samples from monitoring wells MW-103, 

MW-104, and MW-105 also may be affected by 

leachate from the landfill. These wells probably monitor perched water in the tailings, and samples from 

them may not represent actual ground-water quality 

conditions within the tailings. Monitoring well MW103 was located within a drainage ditch, and surface 

runoff may have entered the well during storm events. 

In addition, the filter pack extended to within 5 ft of 

the land surface, which also may have allowed surface 

contaminants to enter the well. Monitoring well MW104 is located adjacent to the old drainage tower (originally clogged with trash and debris) and settling pond 

behind the new drainage structure, both of which may 

affect the water quality in this well. Although MW105 is downgradient from the landfill, the number of 

samples is not sufficient to conclude if leachate affects 

this well.

Although samples from monitoring well MW101 contained mean ranks of Ca and Alk(IT) larger 

than background (fig. 19), mean ranks of other indicator constituents (Na, Cl, NH3t, Ba, and Fe) were not 

significantly larger than those in monitoring well 

MW-100 and, in the case of Na and Ba, were significantly smaller than those in MW-100. A ground-water 

trough lies between this well and the sanitary landfill 

(fig. 12), and the water quality of this well probably 

has not been affected by contaminants migrating 

through the saturated zone from the landfill. The variable water quality of this well may be related to the 

infiltration of pooled runoff from the northern part of 

the sanitary landfill or complex flow within perched 

zones in the tailings.

The water quality of samples from seeps G and 

H has been affected indirectly by the landfill. Specific 

conductance values and concentrations of indicator 

constituents in samples from seep G decreased with 

time (table 13) after demolition and removal of trash 

and other debris from the area around the original 

drainage tower adjacent to monitoring well MW-104 

in 1989. This decrease indicates the source of at least 

part of the contaminants in the original samples from 

this seep collected by the Missouri DGLS and Missouri DEQ was the trash and debris around the drainage tower. After the new drainage structure was 

installed and the tailings excavated to bedrock behind 

the tailings dam in this area, both seeps have gone dry. 

However, several small orange seeps along bedding

62 Hydrogeology and Water Quality at the St Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
planes inside the diversion tunnel, including seep 

10+07, continue to flow.

Bedrock and Mines

Data collected during this investigation indicate 

that landfill leachate has affected water quality in the 

upper bedrock. Results of the ANOVA indicate mean 

ranks of Na, Cl, and Ba in samples from piezometer 

208-P are significantly larger than those from the 

background piezometers completed in bedrock (fig. 

20). The presence of increased Na and Cl concentrations indicates leachate from the landfill has affected 

the bedrock water quality in this area. The magnitude 

of the effect, however, is smaller than the effect in the 

overlying tailings. For example, the concentration of 

Cl and diazinon in samples from piezometer 208-P 

(44-45 mg/L and 2 ng/L) are less than one-half of 

those concentrations in samples from piezometer 108- 

P (95-110 mg/L and 11 ng/L; tables 9 and 11). The 

lack of detectable tritium (less than 5.7 pCi/L) in a 

sample from piezometer 208-P indicates that the component of recent (post-1952) water that contains landfill contaminants near this well is small.

Water-quality data from piezometer 2023-P 

probably indicate the effects of landfill leachate. This 

piezometer lies downgradient of part of the sanitary 

landfill and south of the demolition fill (fig. 5). A sample from this piezometer contained larger than background concentrations of several indicator constituents 

(Na, Cl, NH3t, and Ba), and small specific conductance (818 |iS/cm) and concentrations of Ca (46 mg/L) 

and Alk(IT) (286 mg/L; table 9). The small specific 

conductance value indicates most of this water is not 

derived from the mines or the tailings. The small concentrations of Ca may indicate the precipitation of 

CaCO3 as CC^-rich landfill leachate mixes with ambient ground water. Although this piezometer lies downgradient of the septic tank and drain field immediately 

north of the landfill office, the most likely source of 

contamination is landfill leachate. The concentrations 

of Cl and NH3t in samples from piezometer 2023-P 

were larger than those in samples from piezometer 

208-P even though piezometer 2023-P is 600 ft farther downgradient. A measurable landfill leachate 

effect at piezometer 2023-P indicates preferential lateral transport along bedding planes or horizontal fractures in the bedrock. The available water-level and 

water-quality data indicate that landfill leachate 

detected at piezometer 2023-P could eventually discharge to the diversion tunnel or the mines in the 

vicinity of piezometer 2023-P and the landfill well 

before reaching domestic wells southwest of the landfill site (fig. 14). Leachate contaminants entering the 

mine could affect the water quality of the landfill well.

Samples from piezometer 204-P (fig. 5) contained mean ranks of Cl and Ba significantly larger 

than background and detectable concentrations of 

diazinon (3 ng/L); however, no VOC were detected in 

samples from this piezometer. Probable sources of the 

increased constituent concentrations include leachate 

migrating from the sanitary landfill southward through 

the bedrock, infiltration of contaminated water ponded 

behind the south tailings dam and original discharge 

into the bedrock, or effluent from the septic tank and 

drain field migrating down the original land surface to 

the water table north of piezometer 204-P. The most 

probable source is migration of leachate from the landfill to the south.

The larger than background concentrations of 

Na (40 mg/L), Cl (16 mg/L), and NO2+NO3t (4.8 

mg/L) in the sample from the domestic well south of 

the landfill office are anomalous. The small specific 

conductance value (862 |iS/cm) indicates the well is 

not completed in the abandoned mines. The wellhead 

is buried and is in the vicinity of at least one septic 

tank and drain field, and the increased Na, Cl, and 

NO2+NO3t concentrations probably are related to 

effluent from this source and not landfill leachate.

Concentrations of Na, K, Cl, NH3t, Ba, and B in 

samples from seep 10+07 increased dramatically 

between 1990 and 1993 while concentrations of Ca, 

Mn, SO4, and Zn decreased. Although the potentiometric surface map (fig. 12) indicates the potential for 

flow from the landfill toward the southwest where this 

seep is located, the increased concentrations probably 

are the result of effluent from the septic tank and drain 

field behind the landfill office that lie directly above 

the diversion tunnel and seep 10+07. The increase in 

constituent concentrations coincides with the installation of a septic tank and drain field in 1992. This seep 

is more than 1,000 ft from the sanitary landfill and 

more than 500 ft from the demolition fill.

The migration of leachate from the landfill also 

has affected the water quality in the bedrock northeast 

of the landfill between the sanitary landfill and the Big 

River. The larger than background concentrations of 

several indicator constituents (Na, Alk^), Cl, NH3t, 

and Ba) and increased concentrations of K, 

NO2+NO3t, Li, and Sr in the sample from piezometer

Effects of the Landfill on Water Quality 63
2021-P indicate the movement of landfill leachate into 

the bedrock in this area. The altitude of the bottom of 

the screened interval and filter pack in this piezometer 

(704.52 ft) is more than 30 ft above the Big River, and 

landfill contaminants in this area are expected to move 

toward the Big River. Although concentrations of K, 

NH3t, Ba, and Fe in the sample from piezometer 

2020-P were larger than background, the small concentrations of Na (2.7 mg/L) and Cl (3.5 mg/L) indicate that substantial effects from the landfill are 

unlikely in this area.

No direct effects from the landfill on the water 

quality of the abandoned mines were detected during 

this investigation. However, the presence of a groundwater mound within the tailings and shallow bedrock 

beneath the landfill, the occurrence of landfill leachate 

effects within the tailings and shallow bedrock, the 

presence of relatively recent (post-1952) recharge in 

the mine cavities as evidenced by detectable tritium 

(29 pCi/L) in the landfill well, and the presence of 

potentially open abandoned exploration drill holes 

beneath the tailings pile and landfill indicate some 

downward movement of water and contaminants from 

the landfill into the mine cavities is possible. The 

mean ranks of B a in samples from monitoring well 

MW-303 were significantly larger than those at the 

background mine cavity site at the Baker Mine (fig. 

21). Also, the mean ranks of B in samples from monitoring well MW-303 were significantly larger than the 

background mine cavity site at the Baker Mine (not 

shown in fig. 21; no data were available from the drill 

hole). The increased B concentrations could indicate 

B-rich water in the tailings is migrating into the mine 

cavities. In addition, the small concentration of diazinon (6 ng/L) detected in a sample from monitoring 

well MW-303 may indicate the migration of landfill 

contaminants into the mines; however, additional data 

are needed to confirm this hypothesis. Contaminants 

migrating from the landfill probably would not affect 

the water quality of the abandoned mines in the vicinity of the River Mines well or the water quality of the 

Desloge well. Once in the mine cavities, contaminants 

would enter the regional flow system and migrate to 

the north away from the River Mines well. The lack of 

a well-developed connection between the Desloge 

well and the mine cavities, as evidenced by the large 

differences in water levels in this well and the abandoned mine cavities during installation of this well in 

1972, indicates the water quality of this well is not 

likely to be affected by the landfill.

The concentrations of TCA, 1,1-DCE, cis-DCE, 

TCE, PCE, and MTBE detected in samples from monitoring well MW-303 and the landfill well are anomalous. Potential sources include landfill leachate, spent 

solvents used in the landfill maintenance shop adjacent 

to the landfill well, and localized sources (underground maintenance facilities and abandoned equipment) within the mines. Except for trichlorofluoromethane, cis-DCE, and MTBE, the distribution 

of VOC in samples from monitoring well MW-303, 

the landfill well, and tailings monitoring wells and piezometers contaminated by landfill leachate (MW106, MW-107, 108-P, and MW-109) are different, 

indicating some sources other than landfill leachate. 

Underground sources within the mines probably are 

responsible for at least part of these compounds, 

because background samples from the Baker Mine 

well and samples from the River Mines well contained 

detectable concentrations of PCE and MTBE. Based 

on the available data, however, sources from the landfill cannot be ruled out. If the landfill is the source for 

part of the VOC contamination in the mines cavities at 

the landfill site, the general lack of detection of these 

compounds in the bedrock may indicate discrete paths 

of migration, such as through the exploration drill 

holes.

Surface Water

The available data indicate that the landfill probably has not substantially affected the water quality of 

the Big River; however, additional data at low-base 

flow would be needed for further evaluation. Samples 

collected from the Big River upstream and downstream of the landfill in October 1993 did not contain 

substantial differences in concentrations of indicator 

constituents. However, discharges during this sampling event were about 10 times the estimated 7-day 

2-year low flow of about 12 ft3/s (Skelton, 1976), and 

landfill effects would have been minimized by dilution. Although the sample downstream of the landfill 

contained larger concentrations of 804, NO2+NO3t, B, 

Zn, and Znt than the upstream sample, the differences 

generally are within the range of analytical error. 

Increased concentrations of constituents at the downstream site also could be caused by inflow from the 

abandoned mines, seeps from the tailings pile unrelated to the landfill, or inflow from tributaries between 

the upstream and downstream sampling sites. 

Increased concentrations of SO4 and Zn are common

64 Hydrogeology and Water Quality at the St Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
in seeps from tailings piles and the abandoned mines 

in the region. Smith and Schumacher (1991) concluded that increases in SO4 and Zn concentrations in 

the Big River downstream of the Desloge tailings pile 

were caused by inflow from the abandoned mines. 

Trace element concentrations in samples from MineA-Joe Creek downstream of the landfill tended to be 

larger than in upstream samples; however, no paired 

upstream and downstream samples were collected during this investigation because the creek was either dry 

or flowing at discharges too large to obtain samples 

safely. Data collected by Smith and Schumacher 

(1991) downstream of the landfill indicate constituent 

concentrations were within the range expected for 

seeps from tailings and mined areas.

SUMMARY AND CONCLUSIONS

A multi-phased investigation of the hydrogeology and water quality in the vicinity of the St. Francois County Landfill was conducted by the U.S. 

Geological Survey in cooperation with the St. Francois County Environmental Corporation. The landfill 

is located within an abandoned lead-mine tailings pile 

and was operated from 1973 to 1993. Two temporary 

piezometers and 13 monitoring wells and piezometers 

were installed at the landfill site to determine the 

direction of ground-water flow and ground-water quality at the landfill site. A regional potentiometric map 

of the St. Francois aquifer was prepared to determine 

the relation between shallow ground-water flow at the 

landfill site and the regional ground-water flow system. In addition to onsite studies, a laboratory investigation was conducted to determine the quantity of 

trace elements mobilized from the tailings by landfill 

leachate.

The youngest bedrock unit beneath the landfill 

and tailings pile is the Bonneterre Formation, consisting primarily of dolostone, which was host to the vast 

lead deposits of the Old Lead Belt of southeastern 

Missouri. In southeastern Missouri, the Bonneterre 

Formation and underlying Lamotte Sandstone comprise the St. Francois aquifer, which is used extensively for domestic and public-water supplies in the 

region. The Bonneterre Formation crops out extensively throughout the Old Lead Belt region and locally 

is a leaky confining unit impeding the downward 

movement of water into the underlying Lamotte Sandstone. Water levels in the lower Bonneterre Formation 

and Lamotte Sandstone indicate ground-water flow in

the region generally is toward the north with the Big 

River as the primary drain. About 8 square miles of 

the region are underlain by abandoned, water-filled 

mine cavities. The abandoned mines generally are less 

than several hundred feet below the surface and are 

used locally for domestic and occasionally as publicwater supply.

The mine cavities and Lamotte Sandstone are 

well connected through fractures, joints, and tens of 

thousands of exploration drill holes, and in some areas 

ground water probably is flowing from the mines into 

the Lamotte Sandstone. More than 1,200 exploration 

drill holes were drilled before 1970 on what would 

later become the landfill site 247 lie beneath the sanitary landfill and demolition fill. The water type in the 

St. Francois aquifer in the region ranges from a calcium-magnesium-bicarbonate to a magnesium-bicarbonate water, and water from the Bonneterre 

Formation generally is harder than that from the Lamotte Sandstone. Based on measurements made during 

a regional well inventory, the mean specific conductance value of water from the Lamotte Sandstone was 

566 microsiemens per centimeter at 25 degrees Celsius as compared to 1,017 and 1,160 for the Bonneterre Formation and mine cavities. Concentrations 

of trace elements in samples from public-supply wells 

in the region generally were less than detection levels.

Water-level measurements from monitoring 

wells and piezometers at the landfill site indicate the 

presence of a ground-water mound within the tailings 

and upper bedrock near the center of the site. The 

ground-water mound trends east-west across most of 

the site, the nose of which coincides with the part of 

the buried Mine-A-Joe Creek valley beneath the tailings. In the lower part of the buried valley, the tailings 

are more than 100 feet thick. Within the middle buried 

creek valley, the tailings are saturated to a thickness of 

more than 50 feet. In the northeastern part of the landfill site, recharge moves downward through the refuse 

and tailings to the water table, then down the buried 

Mine-A-Joe Creek valley toward the Big River and the 

abandoned mine cavities about 200 feet below the tailings surface.

Ground water in the tailings, shallow bedrock, 

and mine cavities in the vicinity of the landfill generally has near neutral pH values; specific conductance 

values ranging from 921 to 1,500 microsiemens per 

centimeter; and calcium, magnesium, sulfate, and 

bicarbonate as the predominant dissolved ions. Concentrations of most trace elements generally were less

Summary and Conclusions 65
than a few tens of micrograms per liter. The distribution of trace elements commonly associated with ore 

minerals in the Old Lead Belt, such as cadmium, 

cobalt, lead, nickel, and zinc, in ground water reflects 

the abundance of ore minerals within the tailings and 

bedrock and geochemical reactions that limit their 

aqueous solubilities. Laboratory experiments performed during this investigation indicate that landfill 

leachate, however, may mobilize substantial quantities as much as several hundred micrograms per 

liter of cobalt, copper, lead, and zinc.

Water-quality data indicate the landfill has 

affected the quality of water in the tailings and shallow 

bedrock beneath the site. Landfill leachate has 

migrated from the landfill into the tailings and shallow 

bedrock as evidenced by increased values of specific 

conductance and increased concentrations of calcium, 

sodium, alkalinity, chloride, total ammonia, barium, 

iron, pesticides (diazinon and terbacil), and volatile 

organic compounds (dichloromethane, chlorofluoromethane, dichlorofluoromethane, dichlorodifluoromethane, trichlorofluoromethane, chloroethane, 1,1- 

dichloroethane, vinyl chloride, cis-l,2-dichloroethene, 

trans-l,2,-dichloroethene, and ethyl ether). Although 

laboratory experiments indicated landfill leachate 

could mobilize measurable quantities of trace elements from the mine tailings at the landfill site, concentrations of most trace elements in water samples 

from sites affected by landfill leachate were not significantly larger than background concentrations. Ground 

water in monitoring wells and piezometers affected by 

the landfill was predominantly a calcium-magnesiumbicarbonate type, compared to the calcium-magnesium-sulfate-bicarbonate type typical of ground water 

in the tailings, bedrock, and mine cavities in the 

region. In general, the effects of the landfill were 

greatest in the tailings and Big River alluvium northeast of the landfill.

Samples from monitoring wells MW-106, 

MW-107, and MW-109 generally had the largest values of specific conductance (1,150-2,260 microsiemens per centimeter) and concentrations of the 

following chemical constituents (concentrations in 

milligrams per liter unless noted): calcium (110-356), 

sodium (28-150), total alkalinity (528-1,040), chloride (32-157), total ammonia as nitrogen (2-28), barium (40-371 micrograms per liter), and iron (9- 

29,100 micrograms per liter). Samples from these 

wells also contained the largest concentrations of volatile organic compounds (all concentrations in micrograms per liter), such as dichloromethane (0.3-11), 

chlorofluoromethane (less than 0.2-38), dichlorofluoromethane (less than 0.2-23), dichlorodifluoromethane (less than 0.2-0.4), trichlorofluoromethane 

(less than or equal to 0.2), carbon disulfide (less than 

0.2-1.8), chloroethane (less than 0.2-1.8), vinyl chloride (less than 0.2-0.3), cis-l,2-dichloroethene (less 

than 0.2-16), trans-l,2-dichloroethene (less than or 

equal to 0.2), benzene (less than or equal to 0.2), methyltertiarybutylether (0.3-4.6), and ethyl ether (1.6- 

97). A sample from monitoring well MW-107 contained the largest concentration of the pesticide diazinon (24 nanograms per liter) detected at the landfill 

site. These monitoring wells are completed in the tailings (MW-107), Big River alluvium (MW-106), or 

tailings-Big River alluvium contact (MW-109) near 

the end of the buried creek valley. A predominant 

pathway for leachate migration from the landfill is 

flow through the tailings down this buried valley. 

Except for this area, the available data indicate that 

contaminants from the landfill have not migrated offsite.

Landfill leachate also has entered the shallow 

bedrock beneath the site and seems to be migrating 

through the shallow bedrock toward the Big River 

northeast of the site and southwest toward the landfill 

well. Increased concentrations of sodium, chloride, 

total ammonia, and barium were detected in samples 

from bedrock piezometers 208-P, 2021-P, and 2023- 

P. Except for carbon disulfide (probable degradation of 

xanthates used in the ore flotation process) and drill 

fluid contaminants detected in the initial sample from 

piezometer 208-P (ethylbenzene, xylene, and napthalene), none of the volatile organic compounds detected 

in the tailings were detected in the bedrock.

Although water in the abandoned mine cavities 

beneath the landfill contained detectable concentrations of tritium, indicating a component of recent 

(post-1952) recharge, no direct effects from landfill 

leachate were detected in the mine cavities beneath the 

landfill site. Samples from monitoring well MW-303 

and the landfill well (both completed in the abandoned 

mines), however, contained detectable concentrations 

of several volatile organic compounds (cis-l,2-dichloroethene; 1,1,2-trichloroethene; 1,1,2,2-tetrachloroethene; and methyltertiarybutylether). Samples from the 

landfill well also contained detectable concentrations 

of 1,1,1-trichloroethane and 1,1-dichloroethane. Samples from these wells also contained detectable concentrations of the herbicide prometon (57 and 65

66 Hydrogeology and Water Quality at the St Francois County Landfill and Vicinity, Southeastern Missouri 1990-94
nanograms per liter), and a sample from monitoring 

well MW-303 contained a small concentration of 

diazinon (6 nanograms per liter). Methyltertiarybutylether, 1,1,2,2-tetrachloroethene, and prometon were 

present in background mine water samples from sites 

upgradient of the landfill (Baker Mine and River 

Mines wells). The widespread occurrence of these 

compounds throughout the mine cavities indicates a 

source other than the landfill, such as a nonpoint 

source or multiple localized sources within the mines, 

such as abandoned machinery and supplies. The small 

concentration of diazinon detected in a sample from 

monitoring well MW-303 may indicate the migration 

of landfill contaminants into the mines; however, the 

differences between the distribution of volatile organic 

compounds in samples from this well and the landfill 

well and the tailings wells contaminated by landfill 

leachate (such as monitoring wells MW-106, MW107, and MW-109) indicate some sources for the volatile organic compounds in the mines other than landfill leachate. Additional monitoring is needed, 

however, to confirm this hypothesis. Based on the 

proximity of the site to the Big River, general direction 

of regional ground-water flow, and vast quantities of 

water in the abandoned mines and Lamotte Sandstone, 

it appears unlikely contaminants from the landfill are 

unlikely to affect the water quality of public-supply 

wells in the region.

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and processing of surface-water and bed-materials 

samples for physical and chemical analyses: U.S. Geological Survey Open-File Report 90-140, 71 p.

Wershaw, R.L., Fishman, M.J., Grabbe, R.R., and Lowe, 

L.E., eds., 1987, Methods for the determination of 

organic substances in water and fluvial sediments: U.S. 

Geological Survey Techniques of Water-Resources 

Investigations, book 5, chap. A3, 80 p.

Wright, M.L, andEndicott, Cynthia, 1987, Potentiometric 

map of the deep aquifer, Meramec River Basin, Missouri: Rolla, Missouri Division of Geology and Land 

Survey.

References Cited 69

II
TABLES

T
ABBREVIATIONS AND REPORTING UNITS FOR CHEMICAL CONSTITUE

AND NOTATIONS USED IN TABLE 9

to

a.

O 

o

i

i

o

CO

WL Water level, in feet below top of casing

Q Discharge, in cubic feet per second

SC Specific conductance, in microsiemens per centimeter 

at 25 degrees Celsius

pH In standard units

Temp Water temperature, in degrees Celsius

DO Dissolved oxygen, in milligrams per liter

COD Chemical oxygen demand, in milligrams per liter

Ca Calcium, dissolved, in milligrams per liter

Cat Calcium, total, in milligrams per liter

Mg Magnesium, dissolved, in milligrams per liter

Mgt Magnesium, total, in milligrams per liter

Na Sodium, dissolved, in milligrams per liter

Nat Sodium, total, in milligrams per liter

K Potassium, dissolved, in milligrams per liter

Alk^-p) Alkalinity, total, in milligrams per liter as CaCO3, by incremental titration

HCO3(IT) Bicarbonate, in milligrams per liter, by incremental titration

Alk^gp) Alkalinity, total, in milligrams per liter as CaCO3 , pH 4.5 end point

HCO3(EP) Bicarbonate, in milligrams per liter, pH 4.5 end point

CO3(EP) Carbonate, in milligrams per liter, pH 4.5 end point 

Sulfate, dissolved, in milligrams per liter 

Chloride, dissolved, in milligrams per liter 

Fluoride, dissolved, in milligrams per liter 

Silica, dissolved, in milligrams per liter

Dissolved solids, residue at 180 degrees Celsius, in milligrams per liter 

Dissolved solids, sum of constituents, in milligrams per liter 

Hardness, total, in milligrams per liter as CaCO3 

Organic carbon, total, in milligrams per liter 

Nitrite plus nitrate, dissolved as nitrogen, in milligrams per liter 

Nitrite plus nitrate, total as nitrogen, in milligrams per liter 

Nitrite, dissolved as nitrogen, in milligrams per liter 

Nitrite, total as nitrogen, in milligrams per liter 

Ammonia, dissolved as nitrogen, in milligrams per liter 

Ammonia, total as nitrogen, in milligrams per liter 

Nitrogen, total ammonia plus organic nitrogen as nitrogen, 

in milligrams per liter

TON Nitrogen, total organic, in milligrams per liter

P Phosphorous, dissolved, in milligrams per liter

Pt Phosphorous, total, in milligrams per liter

PO4 Orthophosphate, dissolved, in milligrams per liter

Al Aluminum, dissolved, in micrograms per liter

Sbt Antimony, total, in micrograms per liter

As Arsenic, dissolved, in micrograms per liter

Ast Arsenic, total, in micrograms per liter

<D

c?

3

3 o

<D CO

3

3

i

CO 

0)

0.

2

0

8.

3

S04

Cl

F

SiO2

ROE

TDS

Hard

TOC

NO2+NO3

NO2+NO3t

NO2

N02t

NH3

NH3t

NH3+ONt

Ba

Bat

Be

Bet

B

Bt

Cd

Cdf

Cr

Crt

Co

Cot

Cu

Cut

Fe

Pb 

Pbt 

Li 

Mn 

Mnt 

Hg 

Hgt 

Mo 

Ni 

Nit 

Se 

Set 

Ag 

Agt 

Sr 

Tl 

V 

Vt 

Zn 

Znt 

H 

U 

C 

E

< 

>

Barium, dissolved, in microgra

Barium, total, in micrograms p

Berylium, dissolved, in microg

Berylium, total, in micrograms 

Boron, dissolved, in microgram

Boron, total, in micrograms pe

Cadmium, dissolved, in microg

Cadmium, total, in micrograms 

Chromium, dissolved, in micro

Chromium, total, in microgram

Cobalt, dissolved, in microgram

Cobalt, total, in micrograms pe

Copper, dissolved, in microgra

Copper, total, in micrograms p

Iron, dissolved, in micrograms 

Iron, total, in micrograms per l

Lead, dissolved, in microgram

Lead, total, in micrograms per 

Lithium, dissolved, in microgr

Manganese, dissolved, in micr

Manganese, total, in microgram

Mercury, dissolved, in microgr

Mercury, total, in micrograms 

Molybdenum, dissolved, in mi

Nickel, dissolved, in microgram

Nickel, total, in micrograms pe

Selenium, dissolved, in microg

Selenium, total, in micrograms 

Silver, dissolved, in microgram

Silver, total, in micrograms pe

Strontium, dissolved, in micro

Thallium, dissolved, in microg

Vanadium, dissolved, in micro

Vanadium, total, in microgram

Zinc, dissolved, in micrograms 

Zinc, total, in micrograms per 

Tritium, total, in picocuries pe

U.S. Geological Survey 

Landfill consultant

U.S. Environmental Protection 

No data 

Less than 

Greater than
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity o

Missouri

Site 

T (figs. 2, 5, and 10)

*§. MW-100

o

00

8

0

00

0)

3 

Q.

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21

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3 

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0 

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3

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=

0)

3

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1

5

S

S"

3

5

0

§. MW-1032

<o

9

&

Source

u

u

u

u

u

u

c

u

c

c

c

c

c

c

c

c

c

u

c

u

u

c

c

c

c

c

E

c

c

c

c

c

u

u

u

c

c

c

c

c

c

c

c

c

c

Date

03-30-93

06-22-93

08-05-93

09-09-93

09-28-93

10-27-93

11-04-93

11-24-93

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-27-90

04-27-90

04-30-90

06-07-90

06-28-90

08-09-90

1 1-20-90

02-28-91

04-26-91

06-25-91

08-30-91

05-20-92

08-27-92

11-24-92

02-11-93

03-04-93

03-29-93

06-21-93

11-04-93

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

Time

1745

1930

-

..

1335

1510

-

-

_

-

~

-

-

-

~

1000

1330

0845

~

~

-

.

-

_

~

-

~

-

-

1400

-

-

-

-

-

-

-

-

WL

50.96

50.47

50.4

51.2

50.3

49.8

56.3

49.6

36.2

37.8

28.6

27.7

29.4

^7.15

26.8

27

38.5

33.4

36.2

34.05

25.85

27.2

29.1

38

30

30.8

29.8

28.7

Dry

Dry

Dry

28.2

26.9

25.43

25.2

27.3

15.7

24.8

24.6

25.7

I 25.l

1 26.2

24.1

26.3

Q SC

1,240

1,300

-

..

1,200

1,340

1,110

877

790

915

854

903

1,030

1,150

910

1,275

1,290

1,290

1,220

1,280

1,430

1,540

1,205

1,200

1,230

1,200

_

-

-

-

-

1,470

1,340

675

33,000

1,860

1,420

1,430

1,430

1,630

1,290

1,532

pH

7.6

7.7

-

..

7.5

7.6

7.71

-

7.4

6.9

7.4

7.3

7.3

7.7

7.5

7.2

7.1

6.8

6.83

6.9

6.6

7.4

7.2

7.2

6.5

7.0

7.3

_

-

-

-

-

-

7.4

7.05

7.2

6.8

7.0

7.1

7.0

6.97

6.8

7.05

6.3

Temp

14

14.5

-

..

14

14

13.6

-

_

__

-

-

-

-

-

-

20.5

20.4

17

19

-

-

-

15.2

16.8

_

-

-

-

-

-

15.5

-

_

-

-

-

-

~

-

-

DO 

0.3 

.1 

~

-.

<.5

<.05 

..

--

_

--

-

-

-
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity o

Missouri Continued

Site 

(figs. 2, 5, and 10)

MW- 1032 Continued

3"5

I

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5 

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8

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u

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c

c

c

c

c

c

u

u

c

u

c

c

c

c

c

c

c

c

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Date

04-30-90

04-30-90

06-08-90

06-28-90

08-09-90

11-20-90

02-28-91

04-26-91

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-30-90

06-08-90

06-28-90

06-21-93

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-25-90

06-06-90

06-07-90

09-27-93

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-26-90

06-07-90

Time

1500

__

0730

-

~

-

-

-

-

-

-

--

1600

1000

~

~

-

-

-

-

-

-

1700

1445

~

-

..

__

-

-

-

-

~

-

1100

0930

WL

24.9

27

._

27.7

26.7

Dry

25.7

Dry

-

Dry

Dry

44.4

44.9

44.4

45

44.5

42.5

43.5

Dry

45.4

25

Dry

Dry

26.5

Dry

Dry

Dry

Dry

Dry

28.2

27.3

Dry

30.6

6

! 15.9

6.1

3.3

6.9

U.9

3.9

3.9

5.2

3.9

1.88

Q SC

1,230

1,230

1,140

1,140

1,020

1,040

--

--

809

1,450

1,190

1,670

1,710

1,770

-.

632

-

-

473

-

--

560

-

1,540

1,340

1,430

1,610

1,690

1,645

1,820

1,880

1,940

1,890

1,930

pH

6.3

6.27

5.8

6.5

6.7

6.4

-

~

-

-

7.1

7.1

6.9

7.3

-

6.7

7.2

~

-

7.3

-

--

7.6

-

-

-

-

6.6

-

-

6.7

6.6

6.4

6.6

6.7

6.8

6.7

6.5

6.6

6.5

6.6

Temp DO 

19

19.1

18.5 <0.2

-

--

19

..

-

~

-

--

-

17.5 >1.0 

-

-

16 >1.0 

15.5 .05 
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity o

Missouri Continued

Site 

^ (figs. 2, 5, and 10)

 g. MW-106 Continued

5

(Q

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o

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u

c

u

u

u

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u

u

u

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u

u

u

u

u

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c

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Date

06-28-90

08-09-90

11-20-90

02-28-91

04-26-91

06-25-91

08-30-91

05-20-92

08-27-92

11-24-92

02-11-93

03-04-93

03-30-93

06-23-93

09-29-93

10-28-93

11-04-93

11-24-93

03-04-93

03-30-93

06-23-93

09-09-93

09-29-93

10-28-93

11-04-93

11-24-93

03-04-93

03-29-93

06-23-93

08-05-93

09-09-93

09-28-93

10-27-93

11-24-93

03-04-93

03-31-93

03-31-93

06-22-93

08-05-93

09-09-93

09-29-93

10-28-93

11-04-93

11-24-93

Time

~

_

-

_

-

-

-

0900

0800

0900

1400

-

-

1200

1100

..

0930

1500

-

~

-

1600

1315

-

-

1735

1730

-

1500

1501

1730

~

1030

1320

-

WL

4.2

6

6.5

5.9

5.6

..

4.5

4.3

5.1

4

3.8

4.2

4.2

4.22

2.14

3.4

3.8

2

76.2

77.31

76.28

76.2

76.14

74.58

77.5

75.8

11.5

11.66

11.85

12.4

12.4

10.3

12.1

12

77.6

-

77.48

76.47

77.5

78.4

79.55

77.27

78.3

77.1

Q SC

1,910

1,845

1,580

1,530

1,620

_

1,580

1,750

3330

1,910

1,900

-

1,980

1,960

2,210

2,260

1,990

1,290

1,240

1,150

1,260

1,160

..

1,520

1,540

-

..

1,530

1,530

-

1,580

1,410

..

..

1,370

1,440

1,270

-

pH

6.74

6.8

6.8

6.6

9.3

_

6.9

6.77

38.03

6.95

6.86

-

6.8

7.0

6.7

6.8

6.73

-

-

7.1

7.0

..

7.1

7.0

7.13

--

-

7.6

7.8

-

-

7.6

7.7

~

-

7.1

7.8

-

-

7.1

7.1

7.03

-

Temp

-

__

-

~

15.2

__

18.2

20.2

17.3

13.5

12.7

~

14

16

17.5

17

-

-

17

19

..

16.5

16.5

-

-

-

14.5

14.5

-

-

16

14.5

~

-

15.5

-

16.5

-

-

16.5

16.5

-

-

DO

-

_

-

-

~

0.3

<.05

<.5

.2

-

-

.3

<.05

_

<.5

.2

-

-

-

>1.0

<.05

-

~

<.5

<.05

-

-

.3

-

<.05

-

-

<.5

.2

-
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity 

Missouri Continued

Site 

(figs. 2, 5, and 10)

201 -P

TJ 3"

*»

OOJ.

 o

3

5.

9» 204-P

Q.

O 

O

§

3

3 ±

o

3

(0

0

r: 205-P

0

<3

01

3 

O

O

o

3

as

CD

5> 208-P

5"

ff

3 o

3

1

= 2020-P

(0

01

Q. 2021 -P

TJ

g 2022-P

aCD 2023-P

(0

MW-303

^j

Source

U

u

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u

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u

u

u

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u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

Date

03-04-93

03-29-93

06-22-93

08-05-93

09-09-93

09-28-93

10-27-93

11-24-93

03-04-93

03-30-93

06-22-93

08-05-93

09-09-93

09-28-93

10-27-93

11-24-93

03-04-93

03-30-93

06-22-93

08-05-93

09-09-93

09-28-93

10-29-93

11-24-93

03-04-93

03-29-93

06-23-93

08-05-93

09-09-93

09-28-93

10-28-93

11-24-93

11-24-93

12-21-93

11-24-93

12-20-93

11-24-93

12-21-93

11-24-93

12-21-93

03-04-93

03-29-93

06-22-93

08-05-93

09-09-93

Time

1330

1230

-

-

1030

1115

-

-

1610

1045

-

_.

1500

0950

~

1600

0745

-

_

1600

0815

-

-

1600

1430

-

-

1840

1600

_

0900

1510

-

1100

..

1615

-

1100

1445

~

WL

62.4

61.57

61.3

62.7

64.2

60.71

60.99

58.1

64.9

64.39

63.06

63.4

63.8

64.02

63.58

62.8

52.5

52.38

52.29

52.7

53.4

49.4

52.95

52.1

11.4

11.52

11.75

12

11.4

12.19

11.98

11.9

39.9

41.01

37

36.17

55.4

-

29.3

28.45

79.8

79.45

78.7

79.9

81.5

Q SC

..

1,480

1,500

1,420

1,440

1,010

1,020

..

1,010

990

..

940

930

_

882

909

-

-

903

925

..

957

965

_

1,040

1,360

955

818

950

950

..

PH

7.2

7.1

-

.

6.9

7.1

-

-

7.9

7.3

-

__

7.3

7.5

-

..

7.3

7.3

--'

_

7.3

7.4

--

-

7.3

7.4

-

-

7.4

7.4

..

7.2

7.4

-

7.3

_

7.6

-

7.2

7.3

-

_

Temp DO 

14.5 >1.0 

15 .1 

..

14.5 .5

13.5 <.05 

14 >1.0 

14 4.5 

-

14 <1.0

13.5 <.0 

-

..

15.5 <1.0 

16 2 

-

_

15.5

15 .1 

--

14.5 >1.0 

14.5 3.5 

..

..

14.5 <1.0

13.5 .1 

..

_

14 <.l

14.5 <.5

14.5 <.5

14

-

15.5 <.05 

15.5 .1 

..
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the S

Missouri Continued

00 Site 

(figs. 2, 5, and 10)

^ MW-303 Continued

8

(O

8

o

»< Landfill well

0)

Q.

f?

9

P

£L

0)

Z

9

COr*

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3

3 Baker Mine well

8

CO

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c

5

i- Drill hole6

§

Q.

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0)

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^

3_

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(0

o

F*

2 Domestic well

Source

U

u

c

u

u

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E

U

U

U

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

Date

09-28-93

10-27-93

11-04-93

11-24-93

04-26-90

06-08-90

08-20-92

03-31-93

06-22-93

08-05-93

09-09-93

09-27-93

10-27-93

10-29-93

11-24-93

11-24-93

04-25-90

04-01-93

06-24-93

09-29-93

10-29-93

02-24-88

05-17-88

08-04-88

09-27-88

10-19-88

11-30-88

01-26-89

03-02-89

05-04-89

09-14-89

03-31-93

Time

0825

1330

-

-

1700

0915

1120

0915

0930

._

1730

0815

0930

0915

-

1115

1000

1130

1330

1030

1030

0745

1150

0900

1110

1630

1315

1600

0800

0930

1330

WL

77.95

78.38

72.3

75.5

66.5

62.2

~

69.6

68.83

70.8

71.7

68.11

68.6

_.

65.7

110.6

~

110.55

~

-

-

~

-

__

-

-

-

Q SC

954

1,010

911

-

930

930

756

946

936

938

970

-

1,140

1,080

1,220

954

1,130

0.2 926

.11 921

970

.1 955

.08 944

.11 945

960

.14 950

.14 955

.1 930

862

pH

7.3

7.3

9.18

-

7.1

7

7.1

7.2

7.2

_.

7.3

7.4

_.

-

-

7.1

7.3

7.2

7.4

7.3

7.2

7.5

7.1

7.3

7.2

7.1

7.0

7.0

7.1

6.2

7.3

Temp

15.5

16

-

-

15.5

15.5

-

14

14.5

__

14.5

14.5

..

-

17

15

15.5

15.5

15

12

14.5

21.5

14.5

14

12.5

12

13.5

14

15

14

DO C

<0.5

<.05 <

<

-

<.05 

.2

-

.1 <

.2 <

<.5

.3 <

_

-

.2 

<.05 <

<.05 <

<.5

<.05 <

..

-

-

..

-

-.

-.

>1.0 <
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

Site 

(figs. 2, 5, and 10)

MW-100

TJ

f

8

TJ

3 

 o

(D

3.

w

» MW-101

Q.

O 

0

3

83

3

0

3

(0 

O«*

5"

o

D)

3 

O

O

3

a

?

(D

3

CO5"

0)

D)

3 

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3

3

^

£.

D)

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2

§ MW-1032

aff

to

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Source

U

u

u

u

u

u

c

u

c

c

c

c

c

c

c

c

c

u

c

u

u

c

c

c

c

c

E

c

c

c

c

c

u

u

u

c

c

c

c

c

c

c

c

c

c

Date

03-30-93

06-22-93

08-05-93

09-09-93

09-28-93

10-27-93

11-04-93

11-24-93

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-27-90

04-27-90

04-30-90

06-07-90

06-28-90

08-09-90

11-20-90

02-28-91

04-26-91

06-25-91

08-30-91

05-20-92

08-27-92

11-24-92

02-11-93

03-04-93

03-29-93

06-21-93

11-04-93

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

Mg

120

110

_.

-

120

120

-

-

51

50

-

-

47

-

-

-

63

66

68

79

74

-

-

..

-

~

-

_

25

101

-

-

75

-

-

Mg,

140

120

-

_.

130

150

-

-

..

-

-

..

-

-

-

~

-

__

~

..

~

__

77

-

-

..

-

-

70.2

-

-

-

-

-

Na

9.4

7.5

..

-

7.6

5.9

-

-

1

1

-

-

0

~

-

-

1.4

1.2

3

-

1

<2

~

-

..

-

-

-

-

..

2

2

-

-

-

1

-

-

-

Nat K AlkfTf) HCOsjrr) 

9.2 - 303 370 

7.5 11 288 352 

__

..

11 268 328 

5.3 11.85 294 358 

3.1

..

~

._

..

6.8 321 392 

6 333 407 

_

..

-

__

<2 5

..

--

_

1.8

-

..
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missou ri Conti n ued

° Site 

_ (figs. 2, 5, and 10)

"< MW-1032 Continued

3

(Q

8

o

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D>

3

Q.

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* MW-1044

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u.

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£

<D

£

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3

3

8

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r- MW-1055

g_

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o

c

s

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3

1 MW-106

O

c

I

o

£

Source

U

u

u

c

c

c

c

c

c

c

c

c

c

c

c

c

c

u

u

c

u

c

c

c

c

c

c

c

c

c

u

u

c

u

c

c

c

c

c

c

c

c

c

u

u

Date

04-30-90

04-30-90

06-08-90

06-28-90

08-09-90

11-20-90

02-28-91

04-26-91

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-30-90

06-08-90

06-28-90

06-21-93

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-25-90

06-06-90

06-07-90

09-27-93

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-26-90

06-07-90

Mg

58

..

50

46

_

..

_

_

-

-

-

73

-

--

..

-

-

32

-

-

-

-

-

..

-

24

-

51

50

_

-

-

52

-

-

-

58

58

Mgt Na Na^ K Alk^-p HCO3(|T) 

1.5 - 3.9 346 422

1.2 - 4.3 381 465 

4

..

_

_

..

..

..

3

-

--

..

249 304 

-

1

-

-

..

-

-

-

.9 ~ 2.8 177 216 

28

50

_

..

-

50

..

77 - 28 852 1,040 

66 - 39 926 1,130 
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

Site 

(figs. 2, 5, and 10) Source

MW-106 Continued 

"0

t

8

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C 

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C 

C 

C 

C

U

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U

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u

u

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u

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u

u

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u

u

u

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Date

06-28-90 

08-09-90 

11-20-90 

02-28-91 

04-26-91 

06-25-91 

08-30-91 

05-20-92 

08-27-92 

11-24-92 

02-11-93

03-04-93

03-30-93

06-23-93

09-29-93

10-28-93

11-04-93

11-24-93

03-04-93

03-30-93

06-23-93

09-09-93

09-29-93

10-28-93

11-04-93

11-24-93

03-04-93

03-29-93

06-23-93

08-05-93

09-09-93

09-28-93

10-27-93

11-24-93

03-04-93

03-31-93

03-31-93

06-22-93

08-05-93

09-09-93

09-29-93

10-28-93

11-04-93

11-24-93

Mg

60

75 

66

67

70

71

80

88

~

..

70

66

_

68

69

~

130

120

--

-

130

130

64

68

-

74

73

-

M9,

72

72

67

-

90

68.1

..

_

76

63

_

70

83

-

-

160

120

--

-

-

140

-

90

69

~

-

87

92

-

Na

42

62 

56

74

96

89

96

62

-

_

33

30

_

30

29

~

-

-

63

69

--

--

69

66

-

150

66

-

35

28

-

-

Nat

62

92

84

58

110

..

..

33

29

_

26

30

-

-

61

67

-

--

-

66

150

62

28

19

-

K

32

38

32

25

-

..

-

11

_

10

10.1

--

-

-

14

-

--

15

14.95

..

-

11

12

12.2

-

«< 

~

846

840

935

1,040

~

_

__

623

582

_

588

588

-

-

340

345

-

--

349

328

7646

584

-

-

676

528

-

HCO^

-

1,030

1,030

1,140

1,270

~

760

710

_

718

718

-

-

415

421

--

-

426

401

-

7789

713

-

825

644

-

-
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

Site 

^ (figs. 2, 5, and 10) Source

"§. 201 -P 

o

(Q

8

0

(Q

Q)

3

Q.

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9L

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3

= 205-P

8

(0

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2 MW-303

U 

U

u

u

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u

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u

u

u

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u

u

u

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u

u

u

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u

u

u

u

u

u

u

u

u

Date

03-04-93 

03-29-93

06-22-93

08-05-93

09-09-93

09-28-93

10-27-93

11-24-93

03-04-93

03-30-93

06-22-93

08-05-93

09-09-93

09-28-93

10-27-93

11-24-93

03-04-93

03-30-93

06-22-93

08-05-93

09-09-93

09-28-93

10-29-93

11-24-93

03-04-93

03-29-93

06-23-93

08-05-93

09-09-93

09-28-93

10-28-93

11-24-93

11-24-93

12-21-93

11-24-93

12-20-93

11-24-93

12-21-93

11-24-93

12-21-93

03-04-93

03-29-93

06-22-93

08-05-93

09-09-93

Mg

96

110

93

100

-

69

75

-

-

69

66

~

_

56

58

-

54

55

53

42

-

53

50

..

~

70

63

72

..

48

-

58

58

-

Mg,

120

100

__

110

-

__

1,300

80

-

~

-

76

-

_

58

58

_

-

..

53

-

58

38

~

..

54

..

-

-

~

--

-

_

58

57

Na

14

14

12

12

-

_

15

14

-

-

16

15

-

_

8.9

7.9

_

-

6.6

6.8

35

42

-

..

42

46

_

-

2.7

130

10

_

46

9.4

9.4

Nat

14

15

13

-

15

15

-

~

~

15

-

_

8.5

7.4

..

~

7

34

40

-

47

_.

-

~

-

-

-

..

8.8

9.3

K

1.8

_.

1.9

2.51

-

..

_

1.1

-

-

1.2

1.35

-

_

1.6

_

-

1.6

1.69

-

-

.99

-

_

1

1.11

_.

-

4.6

-

9.8

-

.73

_

4.6

-

3.3

-

Alk(IT)

414

407

238

406

-

7293

298

~

-

294

292

-

_

317

300

_

~

278

279

363

364

~

..

380

373

__

-

366

-

439

340

_

286

-

Til

275

-

HCO3(IT)

505

4%

290

4%

-

.-

7358

364

-

-

359

356

-

_

387

367

~

339

341

443

444

~

464

455

-

447

535

-

415

..

349

--

338

336

-
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

Site 

(figs. 2, 5, and 10)

MW-303 Continued

 o

3-

*tt

<T

9*.

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J

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8

0)

3

Q.

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O

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0

to

3 

O

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? Drill hole6 

J2. s

0

1

3

1

TJ

8

3

3

S Domestic well

2. 35"

0)

Source

U

u

c

u

u

u

E

U

U

U

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

Date

09-28-93

10-27-93

11-04-93

11-24-93

04-26-90

06-08-90

08-20-92

03-31-93

06-22-93

08-05-93

09-09-93

09-27-93

10-27-93

10-29-93

11-24-93

11-24-93

04-25-90

04-01-93

06-24-93

09-29-93

10-29-93

02-24-88

05-17-88

08-04-88

09-27-88

10-19-88

11-30-88

01-26-89

03-02-89

05-04-89

09-14-89

03-31-93

Mg

57

58

-

59

59

-

57

62

__

55

58

-

-

-

74

64

69

58

69

64

65

--

64

65

-

62

61

60

50

MSh

61

59

-

~

-

-

57

56

-

62

-

-

-

~

68

63

-

73

~

-

-

~

-

~

-

~

50

Na

9.6

9.1

-

9

9.5

-

9.1

9.4

..

9.2

9.4

-

~

-

9.8

8.5

8.5

6.1

8.4

9.9

10

-

9.9

11

-

10

9.2

9.6

40

Nat K

2.8

8.4 2.9

18.6

2.8

2.5

..

8.7

10 2.5

2.4

8.4 2.5

..

-

3.1

8.5

8.4 3

5.1

8.8 2.9

3.2

3

2.7

2.8

..

2.9

3.1

2.8

38

«m

238

283

-

276

296

-

276

273

_.

230

271

-

-

~

516

305

280

258

290

-

~

-

-

-

~

~

-

341

HCO^

290

346

-

336

361

-

337

353

280

330

-

-

-

630

372

340

314

353

~

-

-

-

-

~

~

-

416

3 

Q.
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the S

Missouri Continued

* Site 

(figs. 2, 5, and 10)

 < MW-100

5

(O

8

o

(O

0

3

a

0

£ MW-101

£0_

0 *$CD

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3

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U

u

u

u

u

u

c

u

c

c

c

c

c

c

c

c

c

u

c

u

u

c

c

c

c

c

E

c

c

c

c

c

u

u

u

c

c

c

c

c

c

c

c

c

c

Date

03-30-93

06-22-93

08-05-93

09-09-93

09-28-93

10-27-93

11-04-93

11-24-93

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-27-90

04-27-90

04-30-90

06-07-90

06-28-90

08-09-90

11-20-90

02-28-91

04-26-91

06-25-91

08-30-91

05-20-92

08-27-92

11 -24-92

02-11-93

03-04-93

03-29-93

06-21-93

11-04-93

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

SO4

450

500

-

480

473

_

321

350

-

32,329

-

-

_

_

-

508

450

443

-

_

638

-

..

-

-

-

-

-

610

3<10

1,387

-

-

33,165

~

-

-

Cl

3.1

3.2

-

3.3

2.3

_

4

66

1

1

<1

2

43

4

<1

-

3.3

4.3

2

4

2

3

1

-

4

..

-

-

-

-

-

2.1

2

1

1

1

5

2

46

4

<1

F

0.5

.5

-

.5

.58

_

.5

.8

-

__

1.34

-

-

_

-

.4

.3

.44

~

_

<1

-

__

~

-

-

-

.5

.3

.5

-

-

1.35

-

-

SiO2 ROE TDS

9.2 954

9.3 1,040 887

-

..

8.7

8.8 978

808

_

674

671

708

671

680

682

719

766

880

-

9.4

10 - 949

1,060

386

1,075

1,137

1,035

-

1,147

..

-

1,029

474

2,600

1,659

1,202

1,195

1,310

1,158

853

1,149

Hard 

700 

630 

-

730 

710 

1,090 

558 

525 

_

_.

591 

..

..

..

710 

800 

788 

._

-

1,298 

-

..

-

~

..

..

803 

403 

1,164 

-

1,021 

..

..

..
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

Site 

(figs. 2, 5, and 10)

MW- 1 032 Continued

TJ 3-

tO

s

 o

5 

 o

CD

3:

8 MW-1044

0)

Q.

o

8

I5°

3

tO

a

3

O

0)

o"

g MW-1055

3 

(0

s

CD

3

sr

3

(0

0)

3 

 o.

8

if

3

i

(0

» MW-106

Q.

TJ

s0

CD

sr

to

8

Source

U

u

u

c

c

c

c

c

c

c

c

c

c

c

c

c

c

u

u

c

u

c

c

c

c

c

c

c

c

c

u

u

c

u

c

c

c

c

c

c

c

c

c

u

u

Date

04-30-90

04-30-90

06-08-90

06-28-90

08-09-90

11-20-90

02-28-91

04-26-91

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-30-90

06-08-90

06-28-90

06-21-93

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-25-90

06-06-90

06-07-90

09-27-93

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-26-90

06-07-90

SO4

360

_

300

163

~

-

~

~

3 1,251

_

-

-

~

-

3<10

-

_

_.

-

-

~

120

-

3<10

104

-

._

3785

-

-

-

91

150

Cl

2.5

_

4.9

<1

3

4

-

-

9

64

11

44

4

~

--

-

3

-

1

_

-

-

~

.2

-

44

32

3 1

105

86

124

157

109

106

100

78

F SiO2 ROE IDS

0.2 10 - 847

.2 11 808 790

.43 -- - 718

705

897

1,077

929

1.79 - - 923

1,192

_

1,430

..

..

..

.1 - - 233

..

335

_

..

-

.2 2.4 - 344

_

-

.3 - - 471

.7 - - 1,090

990

1,136

1,123

1.49 - - 1,068

1,034

1,033

1,058

.4 18 - 1,110

<.10 19 1,160 1,240

Hard

740

_

660

633

-

-

930

_

-

-

-

-

580

-

_

..

-

-

-

300

-

934

930

~

..

._

826

~

-

-

710

810
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the S

Missouri Continued

°* Site 

(figs. 2, 5, and 10)

«J MW- 106 Continued 

a.

o

(O

0

(O

0)

3

Q.

|

0

9L

SJ.

0

J2

 n

3

O

0.

£ MW-107

0

c

3

ETD)

i

0)

3

a.

jy 108-P

3*

w?

CO 

O

c

s

1

S MW-109

w

o

c-t

T

to

L<o

Source

C

C

C

c

c

E

C

C

C

C

C

u

u

u

u

u

c

u

u

u

u

u

u

u

c

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

c

u

Date

06-28-90

08-09-90

11-20-90

02-28-91

04-26-91

06-25-91

08-30-91

05-20-92

08-27-92

11-24-92

02-11-93

03-04-93

03-30-93

06-23-93

09-29-93

10-28-93

11-04-93

11-24-93

03-04-93

03-30-93

06-23-93

09-09-93

09-29-93

10-28-93

11-04-93

11-24-93

03-04-93

03-29-93

06-23-93

08-05-93

09-09-93

09-28-93

10-27-93

11-24-93

03-04-93

03-31-93

03-31-93

06-22-93

08-05-93

09-09-93

09-29-93

10-28-93

11-04-93

11-24-93

SO4

165

-

150

-

57

..

-

_

100

90

-

340

234

~

84

68

-

47

77

-

360

360

-

-

360

-

220

200

-

-

190

231

Cl

48

77

78

95

90

86

102

3<1

115

114

_

120

120

-

70

106

-

48

48

-

38

51

-

95

110

~

-

100

-

-

35

32

~

37

40

F

0.4

-

-

<1

-

.45

-

_

.4

.4

-

.3

.37

-

-

.3

.3

-

.3

.32

-

-

.7

.7

"

~

-

.7

~

-

.3

~

.3

~

-

-

.3

.33

SiO2

~

-

-

__

..

-

_

17

22

20

20

-

-

16

18

~

15

15

-

-

-

10

10

-

-

9.7

9.5

-

-

19

~

22

~

21

20

-

ROE

-

--

-

__

..

-

_

934

998

-

1,370

~

616

762

-

636

-

-

982

1,050

-

-

-

1,020

-

-

936

912

~

-

842

-

IDS

1,125

1,062

1,026

1,066

1,032

993

1,002

1,060

1,061

1,015

_

1,090

-

~

1,271

-

-

~

713

~

~

656

-

-

_

936

-

~

~

-

_.

872

-

-

-

824

Hard

973

~

-

1,197

-

717

..

-

_

750

690

950

1,200

815

~

620

570

~

580

560

683

-

670

600

-

-

660

660

540

580

-

-

730

680

822
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the S

Missouri Continued

-o

t

s

TO

3

<D

a.

8

0)

3

0.

O

0

iu>

i

0 

3

(0 

O

5"

o

1

o

O

3

1

C 

<D

3

sr

3

0)

1

8

:*

i

i

(0

0)

3 

Q.

TO

8

o

<D

<D

3

S3

Site 

(figs. 2, 5, and 10)

201 -P

204-P

205-P

208-P

2020-P

2021 -P

2022-P

2023-P

MW-303

Source

U

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

Date

03-04-93

03-29-93

06-22-93

08-05-93

09-09-93

09-28-93

10-27-93

11-24-93

03-04-93

03-30-93

06-22-93

08-05-93

09-09-93

09-28-93

10-27-93

11-24-93

03-04-93

03-30-93

06-22-93

08-05-93

09-09-93

09-28-93

10-29-93

11-24-93

03-04-93

03-29-93

06-23-93

08-05-93

09-09-93

09-28-93

10-28-93

11-24-93

11-24-93

12-21-93

11-24-93

12-20-93

11-24-93

12-21-93

11-24-93

12-21-93

03-04-93

03-29-93

06-22-93

08-05-93

09-09-93

SO4

480

520

~

-

490

_

260

260

-

__

260

-

~

200

210

-

-

_

210

_

~

88

110

-

-

92

-

_

250

310

240

60

250

250

-

Ci

8.4

9.7

-

-

9.4

_

17

20

-

17

~

-

11

9.6

-

~

_

7.5

_

-

44

45

-

-

~

44

-

__

3.5

44

-

6.2

-

78

12

12

-

F

<0.10

<10

~

-

<.10

-

_

<10

<.10

<.10

-

<.10

<.10

-

-

_

<10

_

~

.1

.1

-

.1

-

..

<.10

.4

<10

-

.1

.1

.1

-

SiO2

10

9.4

-

-

10

11

~

_

11

12

~

..

12

11

-

-

6.1

6.2

-

-

5.5

5.4

_

-

9.7

10

-

-

10

10

-

..

8.5

15

-

12

-

8.6

9.5

10

-

ROE

1,050

1,240

~

1,150

-

_

800

730

688

-

~

608

670

-

-

_

652

_

~

538

598

-

-

-

570

-

..

_

-

-

-

640

714

-

IDS

1,090

~

-

-

_

658

..

..

-

-

-

584

-

-

_

_

-

532

-

-

_

690

946

645

463

609

-

Hard

820

900

~

-

810

860

-

_

500

550

530

500

-

-

510

510

~

-

500

500

_

-

430

330

-

430

410

~

..

610

530

-

550

-

310

490

490

~
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the S

Missouri Continued

55 Site 

(figs. 2, 5, and 10)

 < MW-303 Continued Q.

3

(Q 

<D

o"

!§ Landfill well

01

a.

i®

O

52.

tt

5

o>

£

 n

3

3 Baker Mine well

o 

o

0)

o

o

3

i- Drillhole6

Q>

Q.

Q>

Q.

5"

3_

5?

2

1

fi Domestic well

Source

U

U

c

u

u

u

E

U

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

Date

09-28-93

10-27-93

11-04-93

11-24-93

04-26-90

06-08-90

08-20-92

03-31-93

06-22-93

08-05-93

09-09-93

09-27-93

10-27-93

10-29-93

11-24-93

11-24-93

04-25-90

04-01-93

06-24-93

09-29-93

10-29-93

02-24-88

05-17-88

08-04-88

09-27-88

10-19-88

11-30-88

01-26-89

03-02-89

05-04-89

09-14-89

03-31-93

SO4

-

240

294

230

240

-

240

240

-

-

240

-

_

350

320

420

~

350

260

270

-

270

-

260

250

260

250

98

Cl

--

12

10.1

12

6.8

-

13

12

-

-

12

-

_

14

13

9.9

-

11

11

9.3

~

11

11

-

11

11

9.7

16

F

-

0.1

.145

<.10

.1

-

.1

.1

-

-

.1

-

-

_

.2

.1

.1

.1

..

_

-

-

-

-

<.10

SiO2

9.6

9.8

-

9.4

9.7

-

9.5

9.9

-

9.9

9.8

-

-

_

9.1

9

9.4

9.2

9.2

9.9

9.9

-

9.6

-

9.9

-

9.7

9.5

9.5

11

ROE

-

684

-

-

665

629

-

606

692

-

-

656

-

_

858

650

940

870

683

693

-

654

-

667

657

665

638

482

TDS

-

493

-

589

617

-

-

620

-

-

-

-

-

_

902

_

819

-

757

649

660

-

653

641

-

627

631

622

Hard

480

510

292

490

520

-

510

530

-

480

510

-

-

_

630

560

610

540

610

560

570

-

540

540

530

530

520

380
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

Site 

(figs. 2, 5, and 10)

MW-100

TJ 3"

o" 

2L

TJ

5 o

CD

5T

o> MW-101

3 

Q.

0 

o

3

3

I

O

3

CO

0

^

0

,2CQ

Q>

3 

O

O

o

3

CO

CD

8"

5"

I o

3

i

CO 

Q>

Q.

TJ

§ MW-1032

3

&0

CO

s

Source

U

U

u

u

u

u

c

u

c

c

c

c

c

c

c

c

c

u

c

u

u

c

c

c

c

c

E

c

c

c

c

c

u

u

u

c

c

c

c

c

c

c

c

c

c

Date NO2 NO^ NH3 NH3t NH3+ONt TON P

03-30-93 - <0.01 - 0.52

06-22-93 - <.01 - .44

08-05-93

09-09-93

09-28-93 - <.01 - .43

10-27-93 - <.01 - .45

11-04-93 - - - .50

11-24-93

01-18-88 -- - 0.2 - -- -- 0.14

05-18-88 - - 1.4 - - - <.05

08-11-88

11-29-88

02-23-89

05-11-89 - - .03 - - - 3.21

08-07-89

11-16-89

02-08-90

04-27-90

04-27-90

04-30-90 <0.01 - .11 -- - -- .11

06-07-90 .02 - .02 .17 0.5 0.33 <.01

06-28-90 - - .51

08-09-90

11-20-90

02-28-91

04-26-91 - - <1

06-25-91

08-30-91

05-20-92

08-27-92

11-24-92

02-11-93

03-04-93

03-29-93

06-21-93

11-04-93 - -- - .13

01-18-88 - - .4 - -- -- <.05

05-18-88 - - .86 - -- - .08

08-11-88

11-29-88

02-23-89

05-11-89 -- - .34 -- -- -- 3 4.12

08-07-89

11-16-89

02-08-90
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

0 Site 

(figs. 2, 5, and 10)

«< MW-1032 Continued

CL

5

CQ

8

o

«<

o>

0.

u

? MW-1044

o

= 2"

~

0

££

 n

3

i

CO

O

o

3

i- MW-1055

o>

Q.

U

0.

oj

3_

5?

CO

o

l-ti

5

2 MW-106

CO 

COo

c

I

<o

0

&

Source

U

u

u

c

c

c

c

c

c

c

c

c

c

c

c

c

c

u

u

c

u

c

c

c

c

c

c

c

c

c

u

u

c

u

c

c

c

c

c

c

c

c

c

u

u

Date NO2 NO* NH3 NH3t NH3+ONt TON P 

04-30-90 <0.01 - 0.04 - - - 0.03 

04-30-90

06-08-90 .01 - .03 - - - <.01 

06-28-90 - - .57 - - - - 

08-09-90

11-20-90

02-28-91

04-26-91

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89 - - .17

08-07-89

11-16-89

02-08-90

04-30-90

06-08-90 - -- - 0.01 2.3 2.3 - 

06-28-90

06-21-93

01-18-88 - - 3 8.5 - -- -- <.05

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-25-90

06-06-90 .02 - .03 .02 .2 .18 .01 

06-07-90

09-27-93

01-18-88 - - .6 -- -- -- <.05

05-18-88 - -- 4.5 - - - <.05

08-11-88

11-29-88

02-23-89

05-11-89 -- - .06 - - - 3.23

08-07-89

11-16-89

02-08-90

04-26-90 <.01 - 21 21 27 6 <.01 

06-07-90 .02 - 25 26 25 0 <.01 
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

Site 

(figs. 2, 5, and 10)

MW- 106 Continued

TJ

f

8

TJ

5

1

CO

CD

3

Q.

O 

O

Q

S

CDo"

3

CO

0

 fc

0

<§ MW-107

3 

O

O

o

i

CD

§f

5"

g 108-P

 o

3

i

CO 

CD

a. MW-109

TJ

CD

8

3

&<j>

CO

(O

Source

C

C

C

C

C

E

C

C

C

C

C

U

u

u

u

u

C

u

u

u

u

u

u

u

C

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

C

u

Date NO2 NO^

06-28-90

08-09-90

11-20-90

02-28-91

04-26-91

06-25-91

08-30-91

05-20-92

08-27-92

11-24-92

02-11-93

03-04-93

03-30-93 - <0.01

06-23-93 - <.01

09-29-93 - <.01

10-28-93 - <.01

H-04-93

11-24-93

03-04-93

03-30-93 - <.01

06-23-93 - <01

09-09-93

09-29-93 - <.01

10-28-93 - <.01

11-04-93

H-24-93

03-04-93

03-29-93 - <.01

06-23-93 - <.01

08-05-93

09-09-93

09-28-93 - <.01

10-27-93 - <.01

11-24-93

03-04-93

03-31-93 - <.01

03-31-93

06-22-93 - .05

08-05-93

09-09-93

09-29-93 - <.01

10-28-93 - <01

11-04-93

11-24-93

NH3 NH3t NH3+ONt TON

16.6

-

36.9

_

-

23.8

_

28

24

23

13

14.5

_

-

2.1

2.2

3

3.4

3.62

.-

4.8

2.4

_

2.3

2.7

-

2

-

2.5

-

-

2.4

2.8

3.02

P

-

-

-

-

0.49

-

-

-

-

..

_

-

-

-

-

-

-

_

-

-

_

-

_-

-

-

-

-
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

M

I

Q.

5

(Q

0

(Q

0)

3

Q.

|

D

9L

 2"

^

0>

(0

r*

 n

3

3

8

(0

po

c

3

sr3

Q.

0)

3

Q.

o"

3

V?

(0

O

c

g

of

5

2

(0 

(0

o

c

I

(O

(O

&

Site 

(figs. 2, 5, and 10)

201 -P

204-P

205-P

208-P

2020-P

202 1-P

2022-P

2023-P

MW-303

Source

U

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

Date NO2 NO*

03-04-93

03-29-93 - <0.01

06-22-93 - <.01

08-05-93

09-09-93

09-28-93 - .03

10-27-93 - .09

11-24-93

03-04-93

03-30-93 - <.01

06-22-93 - <.01

08-05-93

09-09-93

09-28-93 - .1

10-27-93 - .01

11-24-93

03-04-93

03-30-93 - <.01

06-22-93 - .01

08-05-93

09-09-93

09-28-93 - .11

10-29-93 - <.01

11-24-93

03-04-93

03-29-93 - .01

06-23-93 - <.01

08-05-93

09-09-93

09-28-93 - <.01

10-28-93 - .01

11-24-93

11-24-93

12-21-93

11-24-93

12-20-93

11-24-93

12-21-93

11-24-93

12-21-93

03-04-93

03-29-93 ~ <.01

06-22-93 - <.01

08-05-93

09-09-93

NH3 NH3t NH3+ONt TON

_

0.16

.1

-.

.09

.11

__

.02

1.4

.19

.03

_

.02

.59

.05

.02

.-

.06

.1

.18

1

_

1.2

.23

.02

2.5

..

.02

.02

P 

_

__

_

..

_

-

-
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

Site 

(figs. 2, 5, and 10)

MW-303 Continued

TJ

f

8

TJ Landfill well

3

§. $

D)

Q.

83

3

3

o~

3

(0 

O

H Baker Mine well

3

O

3 

O

O

| Drillhole6

a

s

(D

3

5?

3

I

TJ

8

3

3

^ Domestic well

v>

Oi

3

Q.

TJ

§O

3

a®

Source

U

u

c

u

u

u

E

U

U

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

Date NO2 NO^ NH3

09-28-93 ~ <0.01

10-27-93 - <.01

11-04-93

11-24-93

04-26-90 <0.01 ~ <0.01

06-08-90 <.01 ~ .02

08-20-92

03-31-93 -- <.01

06-22-93 - <.01

08-05-93

09-09-93

09-27-93 - <.01

10-27-93 - <.01

10-29-93

11-24-93

11-24-93

04-25-90 <.01 - .03

04-01-93 - <.01

06-24-93 - <.01

09-29-93 - <.01

10-29-93 - <.01

02-24-88

05-17-88

08-04-88

09-27-88

10-19-88

11-30-88

01-26-89

03-02-89

05-04-89

09-14-89

03-31-93 - <.01

NH3t NH3+ONt TON

0.03

.02

.1

<.01 <0.20

-

.01

.01

--

.03

.02

-

.01 <.20

.01

.04

.03

.03

-

_.

..

..

-

-

<.01

P 

..

<0.01 

<.01 

~

_

_-

..

--

<.01 

--

<.001 

__

<.002 

<.001 

<.002 

<.001 
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the S

Missouri Continued

* Site 

_^_ (figs. 2, 5, and 10)

< MW-100

3

(Q

8

o

«<

0)

a

%

9 MW-101

e

=

^

£

<D

J2

 n

3

3

o

(0

O

§

|j.

r

0)

3

a

o>

3

a.

o"

3_

5?

§ 

1

s

3

2

0)

0

c MW-1032

jo

0

g

Source

U

u

u

u

u

u

c

u

c

c

c

c

c

c

c

c

c

u

c

u

u

c

c

c

c

c

E

c

c

c

c

c

u

u

u

c

c

c

c

c

c

c

c

c

c

Date Sbt As Ast

03-30-93 1 - 11

06-22-93 <1 - 18

08-05-93

09-09-93

09-28-93

10-27-93 <1 - 30

11-04-93 ~ - 20

11-24-93

01-18-88 - 4

05-18-88 -- <10

08-11-88

11-29-88

02-23-89

05-11-89 - 22

08-07-89

11-16-89

02-08-90

04-27-90

04-27-90

04-30-90 - <1

06-07-90 - 27

06-28-90 - 11

08-09-90

11-20-90

02-28-91

04-26-91 - <10

06-25-91 <50 <50 <50

08-30-91

05-20-92

OS-21-92

11-24-92

02-11-93

03-04-93

03-29-93

06-21-93

11-04-93 - - 5

01-18-88 - 2

05-18-88 - <10

08-11-88

11-29-88

02-23-89

05-11-89 -- 18

08-07-89

11-16-89

02-08-90

Ba Bat Be

53 50 <0.5

55 50 <1

--

41 - <.5

42 50 <.5

<500

_

50

<50

..

37

_

_

-

19 - <.5

20 - <.5

24

__

_

180

21 21.3 <2

-

<500

40

50

-

52

..

Bet 

2

<1.0 

-

<1.0 

_

-

_

-

_

--

--

_

<2

..

-

..

-
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

Site 

(figs. 2, 5, and 10)

MW-1032 Continued

 o

f

§

 o

3 o

1

to MW-1044

a

O 

o

3

3

3

o"

0)

o

1CO 

01

3 

0

0

3 MW-1055

if*

&5"

I o

a>V)

1

1

<i)

Of

a. MW-106

 o

1

3

&

55

(O

en

Source

U

U

U

c

c

c

c

c

c

c

c

c

c

c

c

c

c

U

U

c

U

c

c

c

c

c

c

c

c

c

U

U

c

U

c

c

c

c

c

c

c

c

c

U

U

Date Sbt As

04-30-90 - 20

04-30-90

06-08-90 - 22

06-28-90 - <10

08-09-90

11-20-90

02-28-91

04-26-91

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-30-90

06-08-90

06-28-90

06-21-93

01-18-88 - <1

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-25-90

06-06-90 - <1

06-07-90

09-27-93

01-18-88 -- 4

05-18-88 - <10

08-11-88

11-29-88

02-23-89

05-11-89 - 7

08-07-89

11-16-89

02-08-90

04-26-90 ~ 27

06-07-90 - 42

Ast Ba Bat Be Bet 

28 - <0.5 - 

__

30 - .5 -4

58 - -- - 

..

..

..

-

_

..

-

--

60 - - - 

..

--

..

-

17 -- .6 - 

..

150 - - - 

80 - - - 

..

..

371 - - - 

_

..

250 - <.5 - 

270 - <.5 - 
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

0 Site 

^ (figs. 2, 5, and 10)

 < MW- 106 Continued

3

(Q

O

(Q

0>

Q.

|

£

=

0>

"Z

<D

(0

r*

Tl

3

3

8

Q MW-107

O

£

r-

§ 

a

«

o>

a

& 108-P

3

V?

O

C

g

1

S MW-109

O

c

I

<0

o

g

Source

C

C

C

C

C

E

C

C

C

c

c

u

u

u

u

u

c

u

u

u

u

u

u

u

c

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

c

u

Date Sbt As

06-28-90 - 49

08-09-90

11-20-90

02-28-91

04-26-91 - 20

06-25-91 <50 <50

08-30-91

05-20-92 - 32

08-27-92

11-24-92

02-11-93

03-04-93

03-30-93 <1

06-23-93 <1

09-29-93

10-28-93 <1

11-04-93

11-24-93

03-04-93

03-30-93 <1

06-23-93 <1

09-09-93

09-29-93

10-28-93 <1

11-04-93

11-24-93

03-04-93

03-29-93 <1

06-23-93 <1

08-05-93

09-09-93

09-28-93

10-27-93 <1

11-24-93

03-04-93

03-31-93 1

03-31-93

06-22-93 <1

08-05-93

09-09-93

09-29-93

10-28-93 <1

11-04-93

11-24-93

As,

-

_

<50

_

-

-

6

9

-

7

<5

39

34

._

~

26

41

~

-

35

14

-

--

13

-

36

41

--

--

.-

27

21

Ba

273

158

191

360

-

-

-

300

270

300

310

_

..

120

110

_

110

110

-

54

57

-

~

44

42

-

44

47

-

-

40

42

-

Bat Be

--

_

199 <2

_

_.

300 <.5

300 <1

<2

300 <2

<500

-

100 <.5

100 <1

_

<.5

100 <.5

<500

-.

50 <.5

50 <1

-

<.5

40 <.5

.-

60 <.5

60 <1

-

-

<5

so * <:5

<500

Bet 

<2

__

.-

..

~

<1.0

<1.0 

<1.0 

_

..

1

<1.0 

_

<1.0 

..

1

<1.0 

<1.0 

<1.0

<1.0 

_.

<1.0 
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

3"

 35

o 

fiJ.

TJ

5 o

5. ~"

8

D)

3

Q.

0 

O

3

3

I6"

3

at

o

5" 

o

D)

3 

O

O

o

I

<D

3

5"

CO

D)

3 o

3

i

at

D)

Q.

TJ

<D

g

3

3

to

Site 

(figs. 2,5, and 10)

201-P

204-P

205-P

208-P

2020-P

2021-P

2022-P

2023-P

MW-303

Source

U

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

Date Sbt As

03-04-93

03-29-93 <1

06-22-93 <1

08-05-93

09-09-93

09-28-93

10-27-93 4

11-24-93

03-04-93

03-30-93 2

06-22-93 <1

08-05-93

09-09-93

09-28-93

10-27-93 6

11-24-93

03-04-93

03-30-93 <1

06-22-93 1

08-05-93

09-09-93

09-28-93

10-29-93 <1

11-24-93

03-04-93

03-29-93 3

06-23-93 <1

08-05-93

09-09-93

09-28-93

10-28-93 1

11-24-93

11-24-93

12-21-93

11-24-93

12-20-93

11-24-93

12-21-93

11-24-93

12-21-93

03-04-93

03-29-93 <1

06-22-93 <1

08-05-93

09-09-93

A$t Ba

4 21

2 22

-

-

20

4 22

..

_

7 26

1 46

43

<1 40

__

..

<1 30

<1 36

--

..

39

<1 37

..

-.

<1 29

2 55

_

~

50

5 44

-

56

100

-

39

-

81

<1 27

2 30

-

Bat Be

..

80 <0.5

20 <1

-

<5

30 <.5

__

50 <.5

50 <1

..

<.5

40 <.5

_

80 <.5

40 <1

--

<.5

40 <.5

-

30 <.5

90 <1

-

-

<.5

100 <.5

~

<1

<1

~

<1

_

<1

..

20 <.5

30 <1

..

Bet 

1

<1.0 

-

..

<1.0 

2

<1.0 

<1.0 

2

<1.0 

--

<1.0 

..

<1.0

<1.0 

-

--

<1.0 

-

-

-

1

<1.0 

-

_-
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

00 Site 

(figs. 2, 5, and 10)

«< MW-303 Continued CL

5

(D

8

o

< LandfiU well

0)

Q.

Si

^

D

=

^

~

(D

J2

Tl

2 

3 Baker Mine well

o

o

CO

o

o

c

3

i- Drill hole6

0)

Q.

0)

3

Q.

<T

3_

«?

0°

C

fi Domestic well

Source

U

u

c

u

u

u

E

U

U

U

U

U

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

Date Sbt As ASf

09-28-93

10-27-93 <1 - <1

11-04-93 - - <5

11-24-93

04-26-90 - <1

06-08-90 - <1

08-20-92 - - <5

03-31-93 <1 -- <1

06-22-93 <1 - <1

08-05-93

09-09-93

09-27-93

10-27-93 <1 - <1

10-29-93

11-24-93

11-24-93

04-25-90 - <1

04-01-93 <1 - <1

06-24-93 <1 - 3

09-29-93

10-29-93 <1 - <1

02-24-88

05-17-88

08-04-88

09-27-88

10-19-88

11-30-88

01-26-89

03-02-89

05-04-89

09-14-89

03-31-93 <1 -- <1

Ba

25

25

-

25

27

-

26

23

-

25

25

-

-

.-

23

24

25

22

20

26

27

27

-

28

-

26

25

27

58

Bat Be

<0.5

30 <.5

<500

<.5

<.5

20 <.5

30 <1

<.5

30 <.5

<.5

20 <.5

20 <1

<.5

30 <.5

<.5

<.5

~

<.5

<.5

<.5

<.5

<.5

50 <.5

Bet 

<1 

-

<1

<1 

<1 

--

-.

<1

<1 

<1 

_

..

-

_

-

-

<1

2

(0

8
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

Site 

(figs. 2, 5, and 10)

MW-100

3-

*w

o

SL

!

a.

» MW-101

Q.

O 

O

3

I5"

3

CO

0

n

0

£

01

3 

O

O

o

3

aSi

s

(D

3

5f

3

0?

3

8

3

i

CO

01

3

Q.

TO

g MW-1032

i

?

CO

Source

U

U

u

u

u

u

c

u

c

c

c

c

c

c

c

c

c

u

c

u

u

c

c

c

c

c

E

c

c

c

c

c

u

u

u

c

c

c

c

c

c

c

c

c

c

Date Cdt

03-30-93 2

06-22-93 <1

08-05-93

09-09-93

09-28-93

10-27-93 <1

11-04-93 7

11-24-93

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-27-90

04-27-90

04-30-90

06-07-90

06-28-90

08-09-90

11-20-90

02-28-91

04-26-91

06-25-91 <5

08-30-91

05-20-92

08-27-92

11-24-92

02-11-93

03-04-93

03-29-93

06-21-93

11-04-93 8

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

Cr

<5

<5

-

<5

<5

-

-

<5

<5

..

-

..

<20

-

-

_

-

<5

<5

<50

-

._

-

<50

<10

-

-

-

_

-

<5

3150

-

-

-

<20

-

-

Crt Co

<5 <3

<5 <3

-

<3

<5 <3

11

-

40

<60

._

_

<20

-

_

9

4

<50

-

-

<50

<10 <10

-

-

__

-

--

_

14

40

^00

-

30

Cot Cu Cut 

<10 <10 <10 

4 <10 <10 

<10 -- 

<3 <10 <10 

43 - 34 

-.

8 - 

9 - 

<20 - 

_

20 - 

<10 -- 

<40 - 

<33 - 

14 <10 <10 

_

_

39 - 33 

4120 - 

<5 - 

<20 - 
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

o Site 

(figs. 2, 5, and 10)

* MW-1032 Continued

Q.

5

(Q

8

o

(Q

D)

Q.

$

{? MW-1044

O

9L

^

S

3 

o

(0

Tl

§

O

o

0>

O 

o

c

3

^ MW-1055

D)

Q.

D)

Q.

<

O

3

(g1

J? O

i

^ MW-106

i

f$

i**

Source

U

u

u

c

c

c

c

c

c

c

c

c

c

c

c

c

c

u

u

c

u

c

c

c

c

c

c

c

c

c

u

u

c

u

c

c

c

c

c

c

c

c

c

u

u

Date Cdt

04-30-90

04-30-90

06-08-90

06-28-90

08-09-90

11-20-90

02-28-91

04-26-91

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-30-90

06-08-90

06-28-90

06-21-93

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-25-90

06-06-90

06-07-90

09-27-93

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-26-90

06-07-90

Cr

<5

<5

<50

--

-

-

--

-

-

-

440

-

-

-

-

-

<5

-

-

-

-

~

-

_

-

<5

_

<5

3 120

-

-

<20

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Physical Properties and Concentrations of Inorganic Constituents In Samples from Wells and Piezometers 101
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

8 Site 

(figs. 2, 5, and 10)

I 201-P

Q.

5

(Q

8

O 

(Q

CO

3 

Q.

^

0)

ff 204-P

Oc 

SL

~r

0)

5

o

!JJ

3 205-P

3

O 

O_

(0

o 

o

c

3

&

CO

Q.

= 208-P

CO

3 

Q.

<

0.

3

^

CO

o

5

g 2020-P

<D

2 2021-P

5"

0 2022-P

a.

1

1 2023-P

(0 

(O

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u

u

u

u

u

u

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u

u

u

u

u

u

u

Date Cdt

03-04-93

03-29-93 4

06-22-93 <1

08-05-93

09-09-93

09-28-93

10-27-93 6

11-24-93

03-04-93

03-30-93 7

06-22-93 <1

08-05-93

09-09-93

09-28-93

10-27-93 <1

11-24-93

03-04-93

03-30-93 <1

06-22-93 <1

08-05-93

09-09-93

09-28-93

10-29-93 <1

11-24-93

03-04-93

03-29-93 1

06-23-93 <1

08-05-93

09-09-93

09-28-93

10-28-93 2

11 -24-93

11-24-93

12-21-93

11-24-93

12-20-93

11-24-93

12-21-93

11-24-93

12-21-93

03-04-93

03-29-93 <1

06-22-93 <1

08-05-93

09-09-93

Cr

-

<5

<5

..

<5

<5

_

-

<5

<5

-

-

<5

<5

-

__

<5

<5

-

<5

<5

--

<5

<5

..

<5

<5

-

<5

-

<5

-

<5

<5

~

<5

<5

-

Crt

~

<5

<5

_.

-

<5

_

-

9

<5

-

-

<5

-

7

<5

-

-

-

<5

~

<5

<5

..

~

5

-

_

-

<5

<5

-

Co

--

20

30

..

-

20

20

-

<3

5

-

4

3

-

<3

<3

-

<3

<3

-

<3

<3

~

<3

<3

-

-

10

-

5

3

<3

-

20

20

-

Cot Cu Cut

-

20 <10 10

20 <10 10

<10

20 <10 15

50 <10 20

8 10 30

-

<10

<3 <10 <10

-

<3 <10 <10

<3 <10 10

<10

<3 10 <10

-

3 <10 <10

<3 <10 <10

<10

<3 <10 <10

-.

<10

11

<10

<10

-

20 <10 <10

20 <10 <10

._
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

Site 

(figs. 2, 5, and 10)

^ MW- 303 Continued

3-

CO

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7 Landfill well

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u

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u

u

u

u

Date Cdt

09-28-93

10-27-93 <1

11-04-93 <5

11-24-93

04-26-90

06-08-90

08-20-92 <1

03-31-93 <1

06-22-93 <1

08-05-93

09-09-93

09-27-93

10-27-93 <1

10-29-93

11-24-93

11-24-93

04-25-90

04-01-93 <1

06-24-93 <1

09-29-93

10-29-93 <1

02-24-88

05-17-88

08-04-88

09-27-88

10-19-88

11-30-88

01-26-89

03-02-89

05-04-89

09-14-89

03-31-93 <1

Cr

<5

<5

-

<5

<5

-

<5

<5

-

~

<5

<5

..

-

-

<5

<5

<5

<5

<5

<5

<5

~

<5

-

<5

~

<5

<5

<5

<5

Crt

-

<5

11

-

-

-

<5

<5

-

-

-

<5

--

-

<5

<5

..

<5

~

-

-

-

-

-

-

-

<5

Co

20

10

-

20

20

-

20

10

-

10

20

..

-

-

20

7

10

<3

10

30

30

-

20

-

30

--

30

20

20

<3

Cot Cu Cut 

<10 - 

20 <10 <10 

17 - 7

<10 - 

<10 - 

..

20 <10 <10 

10 <10 <10 

<10 - 

20 <10 <10 

-

<10 - 

6 <10 11 

10 <10 <10 

<10 - 

10 <10 <10 

<10 - 

<10 - 

<1Q _ 

"

<10 - 

-

<10 - 

<10 - 

<10 - 

<3 <10 - 
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

2 Site 

(figs. 2, 5, and 10)

^ MW-100

Q.

3

(Q

8

0

(Q

0)

3 

Q.

^

ST MW-101

O

c 

SL

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f

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Source

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U

U

u

u

u

c

u

c

c

c

c

c

c

c

c

c

u

c

u

u

c

c

c

c

c

E

c

c

c

c

c

u

u

u

c

c

c

c

c

c

c

c

c

c

Date Pbt

03-30-93 760

06-22-93 53

08-05-93

09-09-93

09-28-93

10-27-93 28

11-04-93 2,360

11-24-93

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-27-90

04-27-90

04-30-90

06-07-90

06-28-90

08-09-90

11-20-90

02-28-91

04-26-91

06-25-91 17

08-30-91

05-20-92

08-27-92

11-24-92

02-11-93

03-04-93

03-29-93

06-21-93

11-04-93 <5

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

Li Mn Mnt Hg Hgt Mo 

28 270 1,300 - <0.1 <10 

29 270 290 - <.l 10 

_

_-

24 250 -- - - 20 

27 240 340 - <.l 10 

3,620 - <.2

88 - 0.3

75 -- <10

._

260 - <.2

__

._

..

13 140 -- -- -- <10 

20 91 -- - - <10 

167 -- 1.1

..

..

-

63 - <.2

100 123 -- - <10 

-

._

._

..

._

-

--

1,020 - <2

263 - .3

191 .. <i

_

_.

140 - <.2

..

-
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

Site 

(figs. 2, 5, and 10)

_ MW-1032 Continued

TJ 3"

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8

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3 MW-1044

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c

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c

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u

c

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c

c

c

c

c

c

u

u

c

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c

c

c

c

c

c

c

c

c

u

u

Date Pb,

04-30-90

04-30-90

06-08-90

06-28-90

08-09-90

11-20-90

02-28-91

04-26-91

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-30-90

06-08-90

06-28-90

06-21-93

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-25-90

06-06-90

06-07-90

09-27-93

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-26-90

06-07-90

Li Mn Mnt Hg Hgt Mo 

11 420 - - - <10 

__

16 430 - - - <10 

399 - 32.7 - - 

-

._

__

500

-

-

<15 3 15 5 

-

.-

-

8 2 - - - <10 

168 - .5 - - 

171 - 1 - - 

_

160 - <.2 - ~ 

-

.-

21 130 - <.l - <10 

28 180 - - -- <10 
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the S

Missouri Continued

o> Site 

(figs. 2, 5, and 10)

I MW-106 Continued

Q.

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80 

(Q

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u

u

u

u

u

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u

u

u

u

c

u

Date

06-28-90

08-09-90

11-20-90

02-28-91

04-26-91

06-25-91

08-30-91

05-20-92

08-27-92

11-24-92

02-11-93

03-04-93

03-30-93

06-23-93

09-29-93

10-28-93

11-04-93

11-24-93

03-04-93

03-30-93

06-23-93

09-09-93

09-29-93

10-28-93

11-04-93

11-24-93

03-04-93

03-29-93

06-23-93

08-05-93

09-09-93

09-28-93

10-27-93

11-24-93

03-04-93

03-31-93

03-31-93

06-22-93

08-05-93

09-09-93

09-29-93

10-28-93

11-04-93

11-24-93

Pbt

_

~

-

..

617

-

-

-

-

-

110

180

--

41

<5

-

350

39

..

_

36

920

-

380

78

-

-

23

-

2,000

-

960

-

320

1,080

Li

_

--

..

-

-

-

-

-

-

-

17

20

32

25

-

-

-

13

13

_.

14

<10

-

5

12

--

10

9

33

23

23

17

~

Mn

248

--

-

-.

117

104

-

211

-

--

-

-

100

92

140

210

-

--

-

95

71

..

67

59

60

52

--

-

53

47

-

120

-

100

140

130

-

Mnt Hg

2.1

-

-

..

.9

164

..

<.2

-

-

--

..

120

96

-

220

173

-

-

260

73

59

944

~

970

74

..

..

68

..

980

..

660

-_

..

460

1,280

Hg, Mo 

-

-

<10 

..

..

-

-

-

..

<0.1 10 

<.l <10 

<30 

<.l <30 

<.2

-

<.l <10 

<.l <10 

<10 

<.l <10 

<.2

~

<.l <10 

<.l <10 

.-

<10 

<.l <10 

--

.2 10 

..

<.l <10 

<10 

.2 <10 

<.2
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

Site 

(figs. 2, 5, and 10)

-o 201-p

31

CO

8

3

!

g

3 204-P

Q.

O

O

S

2-

5"

(0

c^

5" 205-P

o 

(5

0)

3

O

O 

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3 

&d

0

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3

CO

0)

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S

3

3

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« 2020-P

§

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5*

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1

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(0

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3

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u

u

u

u

u 

u

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u

u

u

u

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u

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u

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u

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u

u

u

u

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u

u

u

u

u

u

u

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u

u

u

u

u

u

u

u

u

Date

03-04-93

03-29-93

06-22-93

08-05-93

09-09-93

09-28-93 

10-27-93

11-24-93

03-04-93

03-30-93

06-22-93

08-05-93

09-09-93

09-28-93

10-27-93

11-24-93

03-04-93

03-30-93

06-22-93

08-05-93

09-09-93

09-28-93

10-29-93

11-24-93

03-04-93

03-29-93

06-23-93

08-05-93

09-09-93

09-28-93

10-28-93

11-24-93

11-24-93

12-21-93

11-24-93

12-20-93

11-24-93

12-21-93

11-24-93

12-21-93

03-04-93

03-29-93

06-22-93

08-05-93

09-09-93

Pbt

-

1,200

110

130

..

_

1,100

120

-

-

_

15

13

17

..

-

15

130

18

-

-

25

--

-

~

_.

-

-

~

-

41

140

-

-

Li

-

10

8

_

7 

10

_

6

10

-

-

10

8

-

<4

<4

-.

<4

<4

<4

8

-

-

7

9

-

~

<4

~

18

-

<4

~

<4

-

5

7

-

-

Mn

--

710

720

_

650 

690

__

_

36

100

~

-

100

57

-

3

2

..

<1

2

__

50

62

~

-

78

46

-

610

~

180

-

21

~

53

-

22

17

-

-

Mn, Hg Hgt Mo

-

1,200 - 0.1 <10

720 - <.l <10

690 - <.l <10

_

1,700 - <.l <10

190 - <.l <10

-

<10

54 -- <.l <10

57 - <.l <10

24 - <.l <10

<10

8 - <.l <10

170 -- .3 <10

84 -- <.l <10

-

<10

76 -- <.l <10

-

<10

<10

-

<10

-

<10

22 - .2 <10

110 -- <1 <10

..

..
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

8 Site 

(figs. 2, 5, and 10)

JX. MW-303 Continued

Q.

3

(Q

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u

Date

09-28-93

10-27-93

11-04-93

11-24-93

04-26-90

06-08-90

08-20-92

03-31-93

06-22-93

08-05-93

09-09-93

09-27-93

10-27-93

10-29-93

11-24-93

11-24-93

04-25-90

04-01-93

06-24-93

09-29-93

10-29-93

02-24-88

05-17-88

08-04-88

09-27-88

10-19-88

11-30-88

01-26-89

03-02-89

05-04-89

09-14-89

03-31-93

Pbt

_

41

57

_

-

16

25

27

-

-

28

_

-

_

10

21

-

5

-

..

~

-

-

-

..

4

Li

<4

5

_

_

6

11

<4

8

~

6

5

_

9

4

6

10

7

17

11

11

--

10

-

6

10

8

<4

Mn Mnt Hg Hgt Mo

19 - <io

20 20 - <0.1 <10

9 -- <.2

_

7 -- 0.1 -- <10

9 - .. <io

10 9 - <.l <10

78-- <.l <10

~

..

9 - -- - <10

12 13 -- <.l <10

_

-

160 -- <.l -- <10

55 52 - .1 <10

64 73 ~ <.l <10

42 - -- - <10

64 62 - <.l <10

30 - - -- <10

22 - -- - <10

17 -- -- -- <10

23 - - -- <10

-

21 - -- - <10

19 -- - ~ <10

19 - .. .. <io

<1 1 -- <.l <10
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

Site 

(figs. 2, 5, and 10)

^ MW-100

3-

CO

_

3 o

<D

a.

S MW-101

Q.

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0

8

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CO

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3

3

(D.

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0)

Q.

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0 MW-1032

a

§

^

o

(O

Source

U

u

u

u

u

u

c

u

c

c

c

c

c

c

c

c

c

u

c

u

u

c

c

c

c

c

E

c

c

c

c

c

u

u

u

c

c

c

c

c

c

c

c

c

c

Date Set

03-30-93 <1

06-22-93 <1

08-05-93

09-09-93

09-28-93

10-27-93 <1

11-04-93 <5

11-24-93

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-27-90

04-27-90

04-30-90

06-07-90

06-28-90

08-09-90

11-20-90

02-28-91

04-26-91

06-25-91 <50

08-30-91

05-20-92

08-27-92

11-24-92

02-11-93

03-04-93

03-29-93

06-21-93

11-04-93 <5

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

Ag Agt Sr Tl

<1.0 <1 360 <1

<1.0 <1 310 <1

2 - 290

<1.0 <1 320 <1

<5

3

<5

<20

-

..

__

<1.0 -- 130

<1.0 -- 130

<33

<40

<10 <10 -- <300

~

-

_

..

<5

3

<5

-

<20

..

..

V Vt 

<6 3 

<1 <1 

-

<6 - 

<6 <1 

._

_

-

-

..

._

<6 - 

<6 ~ 

_

<10 <10 

-

-

_

..

-

..

..
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the S

Missouri Continued

o Site 

(figs. 2, 5, and 10)

I MW-1032 Continued

Q.

3

(Q

8

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0)

3 

Q.

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0

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^

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U

u

u

c

c

c

c

c

c

c

c

c

c

c

c

c

c

u

u

c

u

c

c

c

c

c

c

c

c

c

u

u

c

u

c

c

c

c

c

c

c

c

c

u

u

Date

04-30-90

04-30-90

06-08-90

06-28-90

08-09-90

11-20-90

02-28-91

04-26-91

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-30-90

06-08-90

06-28-90

06-21-93

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-25-90

06-06-90

06-07-90

09-27-93

01-18-88

05-18-88

08-11-88

11-29-88

02-23-89

05-11-89

08-07-89

11-16-89

02-08-90

04-26-90

06-07-90

Set

_.

-

-

-

-

-

..

_

~

-

-

-

-

_

~

..

--

~

-

-

-

_.

_

..

-

-

Ag Agt Sr Tl V

<1.0 - 84 -- <6

<1.0 - 76 - <6

<33

..

._

..

-

~

..

<20

..

._

_.

-

..

2

..

..

_

_

..

<1.0 - 22 - <6

5

<5

_

._

<20

..

..

<1.0 - 250 - <6

2 ~ 300 - <6

V, 

-

-

..

-

--

..

370

..

_.

--

..

_

..

--

.-

3

..

1

1

__

..

-
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

Site 

(figs. 2, 5, and 10)

MW-106 Continued

3-

CO

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3

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C

C

C

C

C

E

C

C

C

C

C

u

u

u

u

u

C

u

u

u

u

u

u

u

C

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

C

u

Date Set A9

06-28-90 - <33

08-09-90

11-20-90

02-28-91

04-26-91 - <40

06-25-91 <50 <10

08-30-91

05-20-92 - < 2

08-27-92

11-24-92

02-11-93

03-04-93

03-30-93 <1 <1.0

06-23-93 <1 <1.0

09-29-93 - <3.0

10-28-93 <1 <3.0

11-04-93 6

11-24-93

03-04-93

03-30-93 <1 <1.0

06-23-93 <1 <1.0

09-09-93

09-29-93 - <1.0

10-28-93 <1 <1.0

11-04-93 <5

11-24-93

03-04-93

03-29-93 <1 <1.0

06-23-93 <1 <1.0

08-05-93

09-09-93

09-28-93 - <1.0

10-27-93 <1 <1.0

11-24-93

03-04-93

03-31-93 1 2

03-31-93

06-22-93 <1 <1.0

08-05-93

09.09-93

09-29-93 - <1.0

10-28-93 <1 <1.0

11-04-93

11-24-93

Agt Sr Tl V

_

<10 - <300 <10

_

..

..

<1 310 <1 <6

<1 310 <1 <1

330 -- <18

<1 320 <1 <18

<5

~

<1 290 <1 <6

<1 270 <1 <1

-

240 ~ <6

<1 230 <1 <6

<5

-

-

<1 350 <1 <6

<1 330 <1 <1

..

350 ~ <6

<1 340 <1 <6

_

1 260 <1 <6

_

<1 410 <1 <1

430 - <6

<1 430 <1 <6

..

Vt 

-

<10 

-

_

..

..

<1 

<1 

<1 

~

-

<1 

<1 

-

<1 

-

~

1 

<1 

..

<1 

..

_

2 

_

<1 

..

..

<1 

-
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

 I

ro

I

Q.

5

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0)

3 

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Q.

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(0

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55"

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Site 

(figs. 2, 5, and 10)

201 -P

204-P

205-P

208-P

2020-P

2021 -P

2022-P

2023-P

MW-303

Source

U

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

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u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

u

Date Set Ag

03-04-93 - <5

03-29-93 <1 <1.0

06-22-93 <1 <1.0

08-05-93

09-09-93

09-28-93 - <1.0

10-27-93 <1 <1.0

11-24-93

03-04-93

03-30-93 <1 <1.0

06-22-93 <1 <1.0

08-05-93

09-09-93

09-28-93 - <1.0

10-27-93 <1 <1.0

11-24-93

03-04-93

03-30-93 <1 <1.0

06-22-93 1 <1.0

08-05-93

09-09-93

09-28-93 - 1

10-29-93 1 <1.0

11-24-93

03-04-93

03-29-93 <1 <1.0

06-23-93 <1 <1.0

08-05-93

09-09-93

09-28-93 - <1.0

10-28-93 <1 <1.0

11-24-93

H-24-93

12-21-93 - 1

11-24-93

12-20-93 - 1

11-24-93

12-21-93 - <1.0

11-24-93

12-21-93 - <1.0

03-04-93

03-29-93 <1 <1.0

06-22-93 <1 <1.0

08-05-93

09-09-93

Agt Sr

-

<1 130

<1 110

110

<1 120

-

-

7 130

<1 130

..

130

<1 120

-

_

<1 58

<1 53

-

58

<1 62

_

<1 110

<1 110

--

-

140

<1 130

-

110

290

130

73

-.

<1 92

<1 94

..

-

Tl V

-

<1 <6

<1 <1

_

..

<6

<1 <6

..

-

<1 <6

<1 <1

..

-

<6

<1 <6

-

<1 <6

<1 <1

-

<6

<1 <6

..

._

<1 <6

<1 <1

-

<6

<1 <6

..

1

--

1

1

2

..

<1 <6

<1 <1

-

..

Vt 

<1 

<1 

<1 

..

7 

<1 

..

<1 

<1 

<1 

<1 

<1 

<1 

-

--

<1 

..

-

<1 

<1 

..
Table 9. Physical properties and concentrations of inorganic constituents in samples from wells and piezometers in the vicinity of the 

Missouri Continued

 o

3-

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5 o

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Site

(figs. 2, 5, and 10) Source Date Set A9 A9t

MW-303 Continued U 09-28-93 - <1.0

U 10-27-93 <1 <1.0 <1

C 11-04-93 <5 - <5

U 11-24-93

LandfiUwell U 04-26-90 - <1.0

U 06-08-90 - <1.0

E 08-20-92

U 03-31-93 1 <1.0 <1

U 06-22-93 <1 <1.0 <1

U 08-05-93

U 09-09-93

U 09-27-93 - <1.0

U 10-27-93 <1 <1.0 <1

U 10-29-93

U 11-24-93

U 11-24-93

Baker Mine well U 04-25-90 - <1.0

U 04-01-93 <1 <1.0 <1

U 06-24-93 <1 <1.0 <1

U 09-29-93 - <1.0

U 10-29-93 <1 <1.0 <1

Drillhole6 U 02-24-88 - <1.0

U 05-17-88 -- <1.0

U 08-04-88

U 09-27-88 - <1.0

U 10-19-88

U 11-30-88 - <1.0

U 01-26-89

U 03-02-89 - 1

U 05-04-89 - 1

U 09-14-89 - <1.0

Domestic well U 03-31-93 <1 <1.0 <1

Sr Tl

95

97 <1

..

93

94

91 <1

87 <1

..

..

88

92 <1

._

-

-

110

100 <1

120 <1

110

110 <1

99

100

..

97

_

99

~

100

94

96

89 <1

V

<6

<6

-

<6

<6

<6

<!

-

-

<6

<6

._

-

-

<6

<6

<1

<6

<6

<6

<6

<6

_

<6

<6

<6

<6

<6

Vt 

<1 

<1 

<1 

-

..

<1 

-

-

<1 

<1 

<1 

-

_

~

<1 

1 Original water level listed was depth of water above bottom of well; value was converted to depth below top of casing.

Well was dry during subsequent quarterly sampling events from 06-25-91 through 1 1-24-93 and abandoned in December 1993.

Suspect data not used in statistical analyses.

4 Well was dry during subsequent quarterly sampling events from 06-28-90 through 03-30-93.

5 Well was dry during subsequent quarterly sampling events from 06-28-90 through 09-27-93.

6 Smith and Schumacher (1991).

7 Alkalinity titration performed on a filtered sample.
Table 12. Concentrations of volatile organic compounds detected in water samples from monitoring and public-supply wells, piezome

and quality assurance/quality control samples in the vicinity of the St. Francois County Landfill site, Missouri

[All concentrations are total recoverable and in micrograms per liter, VOC, volatile organic compounds; CS2, carbon disulfide; DCA, 1,1-Dichloroethane; TCA, 1,

1,1-DCE, 1,1-Dichloroethene; cis-DCE, cis-l,2-Dichloroethene; trans-DCE, trans-l,2-Dichloroethene; TCE, 1,1,2-Trichloroethene; PCE, 1,1,2,2-Tetrachloroethene

itaa uuui, , iiu uaiaj

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Date

03-30-93

06-22-93

10-27-93

03-30-93

06-23-93

10-28-93

03-30-93

06-23-93

10-28-93

03-29-93

06-23-93

10-27-93

03-31-93

03-31-93

06-22-93

10-28-93

03-29-93

06-22-93

10-27-93

03-30-93

06-22-93

10-27-93

03-30-93

06-22-93

10-29-93

!03-29-93

06-23-93

10-28-93

05-31-94

03-29-93

06-22-93

10-27-93

Chloro- Dichloro- Dichloro- Trichlorofluoro- fluoro- difluoro- fluoroTotal Chloro- Dichloro- methane methane methane methane 

VOC methane methane (Freon 31) (Freon 21) (Freon 12) (Freon 11) C

0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <

.3 <.2 <.2 <.2 <.2 <.2 <.2 

.4 <.2 <2 <.2 <.2 <.2 <.2 

72 <.2 .4 19 15 <-2 <.2 

102.1 <.2 .3 38 23 <.2 .2 

113.14 <.2 2.3 <.2 <.2 .4 <.2 

27.6 .2 11 7.5 4.1 <.2 <.2 

31.6 <.2 5.4 13 7.3 <.2 <.2 

16.23 <.2 5.9 <.2 <.2 <.2 <.2 

.3 <.2 <.2 <.2 <.2 <.2 <.2 

.9 <.2 .4 <.2 <.2 <.2 <.2 

5 <2 <2 < 2 < 2 < 2 < 2 

17.8 <.2 10 4.5 1.2 <.2 <.2 

20.4 <.2 11 5.5 1.5 <.2 <.2 

24.7 <.2 9 2.6 2.7 <.2 <.2 

21.9 <.2 9.3 <.2 <.2 <.2 <.2 

<.2 <.2 <.2 <.2 <.2 <.2 <.2 

<.2 <.2 <.2 <.2 <.2 <.2 <.2 

<.2 <.2 <.2 <.2 <.2 <.2 <.2 

<2 <.2 <.2 <.2 <.2 <.2 <.2 

<.2 <.2 <.2 <.2 <.2 <.2 <.2 

<.2 <.2 <.2 <.2 <.2 <.2 <.2 

<.2 <.2 <.2 <.2 <.2 <.2 <.2 

<.2 <.2 <.2 <.2 <.2 <.2 <.2 

.4 <.2 <.2 <.2 <.2 <.2 <.2 

1.3 <.2 <.2 <.2 <.2 <.2 <.2 

<.2 <.2 <.2 <.2 <.2 <.2 <.2 

<.2 <.2 <.2 <.2 <.2 <.2 <.2 

<.2 <.2 <.2 <.2 <.2 <.2 <.2 

.9 <.2 <.2 <.2 <.2 <.2 <.2 

.9 <.2 <.2 <.2 <.2 <.2 <.2 

1.4 <.2 <.2 <.2 <.2 <.2 <.2 
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Physical Properties and Concentrations of Inorganic Constituents In Samples from Wells and Piezometers 115
Table 12. Concentrations of volatile organic compounds detected in water samples from monitoring and public-supply wells, pie

and quality assurance/quality control samples in the vicinity of the St. Francois County Landfill site, Missouri Continued

o> Site 

(figs. 2, 5, and 10)

 5 MW-100

i

1Q

fo MW-106

Ctt

3

Q.

§ MW-107

o

1

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5(D

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3

g MW-109 duplicate 

o

CO

O 

o

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iCtt

3 

Q.

= 204-P

Ctt

3 

Q.

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CO,

3

2

g 2022-P

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3.

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<p

Date TCA VC 1,1-DCE cis-DCE trans-DCE TCE

03-30-93 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2

06-22-93 <.2 <.2 <.2 <.2 <.2 <.2

10-27-93 <.2 <.2 <.2 <.2 <.2 <.2

03-30-93 <.2 <.2 <.2 16 .2 <.2

06-23-93 <.2 .3 <.2 14 <.2 <.2

10-28-93 <.2 <.2 <.2 4.7 <.2 <.2

03-30-93 <.2 <.2 <.2 <.2 <.2 <.2

06-23-93 <.2 <.2 <.2 <.2 <.2 <.2

10-28-93 <.2 <.2 <.2 <.2 <.2 <.2

03-29-93 <.2 <.2 <.2 <.2 <.2 <.2

06-23-93 <.2 <.2 <.2 <.2 <.2 <.2

10-27-93 <.2 <.2 <.2 <.2 <.2 <.2

03-31-93 <.2 <.2 <.2 <.2 <.2 <.2

03-31-93 <.2 <.2 <.2 <.2 <.2 <.2

06-22-93 <.2 <.2 <.2 <.2 <.2 <.2

10-28-93 <.2 <.2 <.2 .2 <.2 <.2

03-29-93 <.2 <.2 <.2 <.2 <.2 <.2

06-22-93 <.2 <.2 <.2 <.2 <.2 <.2

10-27-93 <.2 <.2 <.2 <.2 <.2 <.2

03-30-93 <.2 <.2 <.2 <.2 <.2 <2

06-22-93 <.2 <.2 <.2 <.2 <.2 <.2

10-27-93 <.2 <.2 <.2 <.2 <.2 <.2

03-30-93 <.2 <.2 <.2 <.2 <.2 <.2

06-22-93 <.2 <.2 <.2 <.2 <.2 <.2

10-29-93 <.2 <.2 <.2 <.2 <.2 <.2

! 03-29-93 <.2 <.2 <.2 <.2 <.2 <.2

06-23-93 <.2 <.2 <.2 <.2 <.2 <.2

10-28-93 <.2 <.2 <.2 <.2 <.2 <.2

05-31-94 <.2 <.2 <.2 <.2 <.2 <.2

03-29-93 <.2 <.2 <.2 <.2 <.2 <.2

06-22-93 <.2 <.2 <.2 <.2 <.2 <.2

10-27-93 <.2 <.2 <.2 .2 <.2 .2

PCE 

<0.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

< 2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

.5 

.5 

.6 
Table 12. Concentrations of volatile organic compounds detected in water samples from monitoring and public-supply wells, pie

and quality assurance/quality control samples in the vicinity of the St. Francois County Landfill site, Missouri Continued

 o

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Site 

(figs. 2, 5, and 10)

Landfill well

Baker Mine well

Domestic well

Elvins seep at pile

Gumbo well

Desloge well

Park Hills River Mines well

Leadwood No. 1

Leadwood No. 2

Seep 10+07

Big River at Bone-hole

Big River downstream

Equipment blank

Trip blank

Date TCA VC 1,1-DCE cis-DCE trans-DCE TCE

03-31-93 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2

06-22-93 .2 <.2 <.2 <.2 <.2 <.2

10-27-93 .7 <.2 .3 .1 <.2 .2

01-16-94 .7 <.2 <.2 .1 <.2 .2

01-26-94 .7 <.2 .3 .1 <.2 .2

04-20-94 <.2 <.2 <.2 .1 <.2 .15

04-01-93 <.2 <2 <.2 <.2 <.2 <.2

06-24-93 <.2 <.2 <.2 <.2 <.2 <.2

10-29-93 <2 <2 <.2 <,2 <.2 <-2

03-29-93 <.2 <.2 <.2 <.2 <.2 <.2

03-31-93 <.2 <.2 <.2 <.2 <.2 <.2

06-24-93 <.2 <.2 <.2 <.2 <.2 <.2

04-20-94 <.2 <.2 <.2 <.2 <.2 <.2

04-20-94 <.2 <.2 <.2 <.2 <.2 <.2

11-24-93 <.2 <.2 <.2 <.2 <.2 <.2

04-20-94 <.2 <.2 <.2 <.2 <.2 <.2

04-20-94 <.2 <.2 <.2 <.2 <.2 <.2

04-20-94 <.2 <.2 <.2 <.2 <.2 <.2

06-24-93 <.2 <.2 <.2 <.2 <.2 <.2

10-26-93 <.2 <.2 <.2 <.2 <.2 <.2

10-26-93 <.2 <.2 <.2 <.2 <.2 <.2

04-01-93 <.2 <.2 <.2 <.2 <.2 <.2

06-23-93 <.2 <.2 <.2 <.2 <.2 <.2

03-31-93 <.2 <.2 <.2 <.2 <.2 <.2

04-01-93 <.2 <.2 <.2 <.2 <.2 <.2

06-24-93 <.2 <.2 <.2 <.2 <.2 <.2

10-28-93 <.2 <.2 <.2 <.2 <.2 <.2

11-24-93 <.2 <.2 <.2 <.2 <.2 <.2

01-21-94 <.2 <.2 <.2 <.2 <.2 <.2

04-20-94 <.2 <.2 <.2 <.2 <.2 <.2

PCE 

0.5 

.4 

.6 

.6 

.6 

.55 

<.2 

<.2 

.1 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

.1 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<.2 

<2 
Table 12. Concentrations of volatile organic compounds detected in water samples from monitoring and public-supply wells, piez

and quality assurance/quality control samples in the vicinity of the St. Francois County Landfill site, Missouri Continued

» Site 

(figs. 2, 5, and 10)

 <" MW-100

Q.

5

(Q

1

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Date Xylenes Toluene Napthalene MTBE

03-30-93 <0.2 <0.2 <0.2 <0.2

06-22-93 <.2 <.2 <.2 <.2

10-27-93 <.2 .1 <.2 <.2

03-30-93 <.2 <.2 <.2 2

06-23-93 <.2 <.2 <.2 2.1

10-28-93 <.2 <.2 <.2 4.6

03-30-93 <.2 <.2 <.2 .8

06-23-93 <.2 <.2 <.2 .9

10-28-93 <.2 <.2 <.2 .7

03-29-93 <.2 <.2 <.2 .1

06-23-93 <.2 <.2 <.2 <.2

10-27-93 <.2 <.2 <.2 <.2

03-31-93 <.2 <.2 <.2 .3

03-31-93 <.2 <.2 <.2 .3

06-22-93 <.2 <.2 <.2 .3

10-28-93 <.2 <.2 <.2 .4

03-29-93 <.2 <.2 <.2 <.2

06-22-93 <.2 <.2 <.2 <.2

10-27-93 <.2 <.2 <.2 <.2

03-30-93 <.2 <.2 <.2 <.2

06-22-93 <.2 <.2 <.2 <.2

10-27-93 <.2 <.2 <.2 <.2

03-30-93 <.2 <.2 <.2 <.2

06-22-93 <.2 <.2 <.2 <.2

10-29-93 <.2 <.2 <.2 <.2

! 03-29-93 .5 <.2 .6 <.2

06-23-93 <.2 <.2 <.2 <.2

10-28-93 <.2 <.2 <.2 <.2

05-31-94 <.2 <.2 <.2 <.2

03-29-93 <.2 <.2 <.2 .4

06-22-93 <.2 <.2 <.2 .4

10-27-93 <.2 <.2 <.2 .4

Ethyl ether Acetone

<0.2 <5

<.2 <5

<.2 <5

18 <5

23 <5

97 <5

4 <5

4.8 <5

9.5 <5

<.2 <5

<.2 <5

<.2 <5

1.6 <5

1.9 <5

9.9 <5

10 <5

<.2 <5

<.2 <5

<.2 <5

<.2 <5

<.2 <5

<.2 <5

<.2 <5

<.2 <5

<.2 <5

<.2 <5

<.2 <5

<.2 <5

<.2 <.2

<.2 <5

<.2 <5

<.2 <5

2-Butanone

<5

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<5

<5

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Physical Properties and Concentrations of Inorganic Constituents in Samples from Wells and Piezometers 119
ABBREVIATIONS AND REPORTING UNITS FOR CHEMICAL CONSTITUENTS 

AND NOTATIONS USED IN TABLE 13

(Q

o

(Q

0>

O

2J.

S 

o>

CO

Q 

SC

PH

Temp

DO

COD

Ca

Mg 

Mft

Na

K

HCO3(rT)

0

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CO3(EP) 

S04

Cl

F

SiO2 

ROE 

TDS

Hard 

TOC

NO2+NO3 

NO2+NO3t

NO2

N02t 

NH3

NH3t

NH3+ONt

TON

P

Pt

P04

Al

Sbt

As

Ast

Discharge, in cubic feet per second

Specific conductance, in microsiemens per centimeter

at 25 degrees Celsius 

In standard units

Water temperature, in degrees Celsius 

Dissolved oxygen, in milligrams per liter 

Chemical oxygen demand, in milligrams per liter 

Calcium, dissolved, in milligrams per liter 

Calcium, total, in milligrams per liter 

Magnesium, dissolved, in milligrams per liter 

Magnesium, total, in milligrams per liter 

Sodium, dissolved, in milligrams per liter 

Sodium, total, in milligrams per liter 

Potassium, dissolved, in milligrams per liter

Alkalinity, total, in milligrams per liter as CaCO3 , by incremental titration 

Bicarbonate, in milligrams per liter, by incremental titration 

Alkalinity, total, in milligrams per liter as CaCO3, pH 4.5 end point 

Bicarbonate, in milligrams per liter, pH 4.5 end point 

Carbonate, in milligrams per liter, pH 4.5 end point 

Sulfate, dissolved, in milligrams per liter 

Chloride, dissolved, in milligrams per liter 

Fluoride, dissolved, in milligrams per liter 

Silica, dissolved, in milligrams per liter

Dissolved solids, residue at 180 degrees Celsius, in milligrams per liter 

Dissolved solids, sum of constituents, in milligrams per liter 

Hardness, total, in milligrams per liter as CaCO3 

Organic carbon, total, in milligrams per liter 

Nitrite plus nitrate, dissolved as nitrogen, in milligrams per liter 

Nitrite plus nitrate, total as nitrogen, in milligrams per liter 

Nitrite, dissolved as nitrogen, in milligrams per liter 

Nitrite, total as nitrogen, in milligrams per liter 

Ammonia, dissolved as nitrogen, in milligrams per liter 

Ammonia, total as nitrogen, in milligrams per liter 

Nitrogen, total ammonia plus organic nitrogen as nitrogen,

in milligrams per liter

Nitrogen, total organic, in milligrams per liter 

Phosphorous, dissolved, in milligrams per liter 

Phosphorous, total, in milligrams per liter 

Orthophosphate, dissolved, in milligrams per liter 

Aluminum, dissolved, in micrograms per liter 

Antimony, total, in micrograms per liter 

Arsenic, dissolved, in micrograms per liter 

Arsenic, total, in micrograms per liter

Ba Barium, dissolved, in microgr

Bat Barium, total, in micrograms p

Be Berylium, dissolved, in microg

Bet Berylium, total, in microgram

B Boron, dissolved, in microgram

Bt Boron, total, in micrograms pe

Cd Cadmium, dissolved, in micro

Cdt Cadmium, total, in microgram

Cr Chromium, dissolved, in micr

Crt Chromium, total, in microgram

Co Cobalt, dissolved, in microgra

Cot Cobalt, total, in micrograms p

Cu Copper, dissolved, in microgra

Cut Copper, total, in micrograms p

Fe Iron, dissolved, in micrograms 

Fe* Iron, total, in micrograms per 

Fe Ferric iron, dissolved, estimat

Pb Lead, dissolved, in microgram

Pbt Lead, total, in micrograms per 

Li Lithium, dissolved, in microgr

Mn Manganese, dissolved, in micr

Mnt Manganese, total, in microgra

Hg Mercury, dissolved, in microg

Hgt Mercury, total, in micrograms 

Mo Molybdenum, dissolved, in m

Ni Nickel, dissolved, in microgra

Nit Nickel, total, in micrograms p

Se Selenium, dissolved, in micro

Set Selenium, total, in microgram

Ag Silver, dissolved, in microgram

Agt Silver, total, in micrograms pe

Sr Strontium, dissolved, in micro

Tl Thallium, dissolved, in microg

V Vanadium, dissolved, in micro

Vt Vanadium, total, in microgram

Zn Zinc, dissolved, in microgram

Znt Zinc, total, in micrograms per 

e Estimated value

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> Greater than

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Physical Properties and Concentrations of Inorganic Constituents in Samples from Wells and Piezometers 121
Table 13. Physical properties and concentrations of inorganic constituents in samples from seeps and surface water in the vicinity 

site, Missouri Continued

Hydrogeol

0

(0

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Site 

(figs. 1 and 5) Date

Big River at Bone-hole 303- 1 8-80

!02-24-88

!05- 17-88

!09-27-88

! 1 1-30-88

1 03-02-89

^5-04-89

1 09- 14-89

h 1-07-89

10-26-93

Big River downstream 303- 1 8-80

41-07-89

10-26-93

Mine-A-Joe Creek upstream ^3- 1 8-80

04-26-90

Mine-A-Joe Creek downstream 203- 1 8-80

303-18-80

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105-17-88

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! 03-02-89

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Time

-

1130

0930

0800

1700

1715

0830

0830

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1500

1200

1615

1230

1230

0830

0930

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0830

1800

0915

0945

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285

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63

271

185

134

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39.3

119

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122

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SC

310

317

509

453

300

377

420

608

622

510

260

640

468

460

1,130

460

460

856

1,235

1,130

1,075

1,010

1,207

478

PH

6.0

8.01

7.39

8.2

8.02

7.89

7.63

6.66

7.85

8.0

6.4

8.07

8.0

7.3

7.3

7.3

8.13

8.61

8.16

7.9

7.99

7.95

7.64

6.43

Temp DO COD

11

7

19

14.5

7

6.5

15

16.5

14.3

12.5 7 <10

10

15.2

13.5 7 <10

6

8

12.4

15.5

12

4.5

7.1

11.9

15

Ca 

-

34

59

48

34

41

45

65

64

50 

_

65

52 

130

_

100

160

150

170

140

120

140

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Physical Properties and Concentrations of inorganic Constituents in Samples from Wells and Piezometers 123
Table 13. Physical properties and concentrations of inorganic constituents in samples from seeps and surface water in the vicinity 

site, Missouri Continued

.£ Site 

g (figs. 1 and 5)

(Q 

§ Big River at Bone-hole

o"

(Q«<

Oi

3

Q.

sr<D^

p

95.

3

s

o 

2

-n

§ Big River downstream

o

o

0)

Oo 

c

3

&

!_ Mine-A-Joe Creek upstream

a>

Date

303- 18-80

!02-24-88

^s-n-ss

1 09-27-88

l l 1-30-88

1 03-02-89

1 05-04-89

1 09- 14-89

1 11-07-89

10-26-93

303- 18-80

1 11-07-89

10-26-93

203-18-80

04-26-90

Na Nat

-

3.1

5

4.1

2.8

3.6

3.7

6.1

5.9

4.1 3.8

5.5

4.2 4.2

15

K Alktrr, HC03(rr,

-

1.4

1.6

1.9

1.5

1.3

1.8

2.2

1.9

1.92 207 252

2

1.98 204 249

_

4.8 286 349

Alk(EP)

-

118

211

195

142

168

179

226

231

208

235

203

HCO3(EP)

-

140

260

240

170

200

220

270

280

-

290

Mine-A-Joe Creek downstream 203-18-80

J03-18-80 

1 02-24-88 

^5-17-88 

1 09-27-88 

2 ll-01-88

12-01-88 

03-02-89 

05-04-89 

09-14-89

13

17

12

13

16

15

9.1

6.3

7.5

6.1

6.9

7.8

7.9

5.4

242

292

184

290

294

305

71

295

337

224

309

358

372

86

Southwest Creek 04-26-90 1.1 280 342 276
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Physical Properties and Concentrations of inorganic Constituents in Samples from Wells and Piezometers 125
Table 13. Physical properties and concentrations of inorganic constituents in samples from seeps and surface water in the vicinity 

site, Missouri Continued

£ Site 

| (figs. 1 and 5)

§ Big River at Bone-hole

o"

5

Q>

3

Q.

|

0

c 

9L

£

0)

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§ Big River downstream

o

o

(0

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3

P. Mine- A- Joe Creek upstream

Q> 

Q.

to 

3 Mine-A-Joe Creek downstream

<

o

3_

^

0

I

a

5

sr

8

Date

303- 18-80

1 02-24-88

05-17-88

1 09-27-88

1 11-30-88

!03-02-89

1 05-04-89

1 09-14-89

1 11-07-89

10-26-93

303-18-80

1 11-07-89

10-26-93

203-18-80

04-26-90

2Q3- 18-80

303-18-80

!02-24-88

los-n-s»

109-27-88

2 ll-01-88

1 12-01-88

1 03-02-89

! 05-04-89

1 09- 14-89

S04

-

39

77

51

38

41

51

110

93

49

100

54

-

320

_

220

480

460

-

350

280

410

180

Cl F

-

4.6

5.3

5.5

3.4

4.4

4.2

6.6

7

5.7 <0.1

7

5.9 <.l

-

14 <.l

_

15

18

14

19

15

18

14

12

Si02

-

5.5

4.8

7.1

7.8

5.5

3.5

9.8

5.4

6

5.4

5.9

-

2.3

_

_

7.2

6.6

6.4

8.5

6.7

5.6

2.7

ROE

-

189

307

260

191

217

249

375

-

276

276

-

-

_

607

969

870

814

724

908

370

TDS

-

179

314

264

192

222

244

375

356

269

364

276

-

722

_

563

959

826

110

776

689

858

337

Hard

-

170

290

240

160

200

220

330

320

240

330

250

-

590

480

780

650

630

560

690

250

Southwest Creek 04-26-90 26 3.6 7.2 302 290
Table 13. Physical properties and concentrations of inorganic constituents in samples from seeps and surface water in the vicinit

site, Missouri Continued

-o Site 

<T (figs. 1 and 5)

8 Elvins tailings pile seep

TJ

5 o

CD

3. 

CD

CO

0)

3

a

O

0

o

i

0

3

CO

o SeepG

o

(3

3 

O

g

3

a

£CD

CO

= SeepH

1 o

CD

CO

:? SeepK

o

3

S. co~

0)

a Seep 10+07

TJ 

8O

i

s>

Date NO2+NO3 NO2+NO3t NO2 NO^ NH3

1 02-23-88

IQO 26 oo

1 11-30-88

1 03-02-89

05-03-89

IHO 1 /i_8o uy-14-oy

03-31-93

03-31-93 - 0.18 -- <0.01

06-24-93 - .05 ~ <.01

203-18-80

303- 18-80

21 1-01-88

1 11-06-89 <0.1 - <0.01 - 0.26

04-26-90 <.l - <.01 - .15

06-07-90 <.l - <.01 - .04

06-07-90 <.l -- <.01 - .07

04-26-90 .1 - <.01 - .14

06-07-90 2.9 ~ .01 - .14

1 ll-07-89 <.l -- <.01 - 6.8

04-26-90 <.l - <.01 - 9

06-07-90 .1 - <.01 - 2.2

06-07-90 <.l - <.01 - .36

03-31-93 - .09

06-24-93 - 1.4 - .03

10-30-93

NHgt NH3+ONt 

-

-

_

0.01

.01

-

-

-.

.13 0.4 

-

.12 .2 

..

_

10 11 

-

-

1.7

2.4

4.8
Table 13. Physical properties and concentrations of inorganic constituents in samples from seeps and surface water in the vicinity 

site, Missouri Continued

o

<Q

Site 

(figs. 1 and 5) Date N02+N03 NO2+NO3t NO2 NO 2, NH3 NH3t NH3+ONt 

g Big River at Bone-hole

O 

<Q

Q> 

3 

Q.

303-18-80 

1 02-24-88 

^5-17-88 

! 09-27-88

1 11-30-88 

1 03-02-89 

^5-04-89

10-26-93 0.05 <0.010 0.02

3 

|

w

c

3

sQ.

Big River downstream

Mine- A- Joe Creek upstream

303-18-80 

l l 1-07-89 

10-26-93

^03-18-80 

04-26-90

.09 <.010 .021

<0.1 <0.01 0.05

Q>

5Q.

(0 

O

Mine-A-Joe Creek downstream

k* 

CO

§

Southwest Creek

^03-18-80 

303-18-80 

! 02-24-88 

^5-17-88 

1 09-27-88

2ll-01-88

12-01-88

1 03-02-89

05-04-89 

09-14-89

04-26-90
Table 13. Physical properties and concentrations of inorganic constituents in samples from seeps and surface water in the vicinit

site, Missouri Continued

 o Site

£ (figs. 1 and 5)

to

2 Elvins tailings pile seep

TJ

3

TJ

a<D

to

0)

3

a

Oo

3

O

§

I

o

3

to 

o SeepG

5"

0

cB0>

3 

O

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I

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3 SeepH

i

T3

$

* SeepK 

o

3

I

to

n>

a Seep 10+07

TJ 

!O

3

*

Date P Pt PO4 Al Sbt As

1 02-23-88 - - - <10

1 09-26-88 <0.001 - 0.003 <10

41-30-88 <.002 - <.001 <10

1 03-02-89 <.001 - <.001 <10

1 05-03-89 <.002 - .002 <10

1 09-14-89 <.001 - <.001 <10

03-31-93

03-31-93 -- 0.02 - - <1

06-24-93 - <02 - - <1

203-18-80

303- 18-80

2 1 1-01 -88 - -- -- - - <5

1 11-06-89 <.01 - <01 <10

04-26-90 <.01 .09 <.01 - - 2

06-07-90 <.01 - <.01 - - <1

06-07-90 <.01 - <.01 - - 2

04-26-90 <.01 <.01 .01 - - 3

06-07-90 <.01 - <.01 - - <1

1 11-07-89 <.01 - .021 20

04-26-90 <.01 <.01 <.01 - - <1

06-07-90 <.01 - <.01 -- - 1

! 06-07-90 .01 - <.01 - - 1

03-31-93

06-24-93 - <02

10-30-93 ~ <02

Ast 

..

2 

<1 

..

..
Table 13. Physical properties and concentrations of inorganic constituents in samples from seeps and surface water in the vicinity 

site, Missouri Continued

£ Site 

1* (figs. 1 and 5)

(O 

§ Big River at Bone-hole

6~

(O

o>

3

Q.

Q>

<D

9L

^

m

o 

to

~n

9J Big River downstream

§CO

O

c

3

!_ Mine- A- Joe Creek upstream

o>

3

Q.

Q>

3 Mine- A- Joe Creek downstream

<

o.

3

V?

0)

O

C

?

0

3

2

o

c

2.

<o Southwest Creek

Date P P, PO4 Al

303- 18-80

^2-24-88 - - - <10

^5-1 7-88 - - -- <10

1 09-27-88 0.008 - 0.003 <10

1 11-30-88 .007 - <.001 <10

1 03-02-89 .009 - .002 <10

^5-04-89 .004 - .002 <10

1 09-14-89 .01 - .006 <10

1 ll-07-89 -- - -- <10

10-26-93 -- 0.13

303- 18-80

hi -07-89 - -- - <10

10-26-93 - .02

203-18-80

04-26-90 <.01 - <.01

^3-1 8-80

303- 18-80

1 02-24-88 - - - <10

^S-H-SS - - - <10

1 09-27-88 <.001 - .003 <10

21 1-01 -88

1 12-01-88 <.002 - <.001 <10

1 03-02-89 .003 -- <001 <10

'05-04-89 <002 -- .002 <10

1 09-14-89 .002 - .001 <10

04-26-90

Sbt As As, 

--

<1 -- <1 

_

<1 -- <1 

..

<1 - 

-

-

<5 - 

<1 -- 
Table 13. Physical properties and concentrations of inorganic constituents in samples from seeps and surface water in the vicinity 

site, Missouri Continued

 o Site 

<< (figs. 1 and 5)

CO

Q> Elvins tailings pile seep

 o

3

S

Q>

3

Q. 

O

O

3

O

CD

S

5"

3

CO

o SeepG

0

cB

Q>

3

O

O 

o

3

CO

CD

3

5T

J SeepH

I

~~

8

^ SeepK

0

3

i

CO

Q>

Q. Seep 10+07

 o

CD

N

O

i

Date Be

1 02-23-88 <0.5

1 09-26-88 <.5

1 11-30-88 <.5

1 03-02-89 <1.5

^S-OS^ <.5

1 09-14-89 <.5

03-31-93

03-31-93 <.5

06-24-93 <1

203-18-80

303-18-80

21 1-01 -88

l l 1-06-89 <1

04-26-90 <.5

06-07-90 <.5

06-07-90 <.5

04-26-90 <.5

06-07-90 <.5

1 11-07-89 <.5

04-26-90 <.5

06-07-90 <.5

06-07-90 <.5

03-31-93 <.5

06-24-93 <1

10-30-93

B^ B

..

_

..

-

_

<1

<1 38

..

..

90

100

100

180

270

..

280

320

80

._

190

-

Bt Cd Cdt

17

21

28

26

15

21

_

46 21 30

42 18 18

4.5 4.6

5

10

<2

<1

14

1

3

5

<1

<1

2

<1

<1

<1

-

Cr 

<5

<5

<5

<10

<5

<5

<5 

<5 

..

..

40

<10

<5

<5

<5

<5

<5

2

<5

<5

<5

<1

<5

-
£ Table 13. Physical properties and concentrations of inorganic constituents in samples from seeps and surface water in the vicinity 

M site, Missouri Continued

£ Site 

§ (figs. 1 and 5)

<Q 

§ Big River at Bone-hole

o~

(Q

0)

3

Q.

3?0)

$

£2.

^

a

(D 

(0

Tl

3 Big River downstream

8

CO

O

o

C 

3

j_ Mine- A- Joe Creek upstream

0)

Q.

Date Be

303- 18-80

1 02-24-88 <0.5

1Q5.17-88 <.5

1 09-27-88 <.5

] 1 1-30-88 <.5

]03-02-89 <.5

1 05-04-89 <.5

1 09-14-89 <.5

] 1 1-07-89 <.5

10-26-93 <.5

303- 18-80

1 11-07-89 <.5

10-26-93 <.5

203-18-80

04-26-90 <.5

Bet B Bt Cd Cdt Cr 

2

<1 - <5

1 - <5

<1 - <5

<1 - <5

<1 - <5

<1 - <5

<1 - <5

1 - <5

<1 16 <20 <1 <1 <5 

3

<1 <5

<1 23 <20 1 <1 <5 

.1 .1

100 - <1 - <5

Mine- A- Joe Creek downstream

o

C

I

<o Southwest Creek

^3-18-80 

303-18-80 

1 02-24-88

1 09-27-88 

2 ll-01-88 

1 12-01-88 

1 03-02-89 

] 05-04-89 

1 09- 14-89

04-26-90 30

<5 

<5 

<5 

<5 

<5 

<5 

<5 

<5

<5
Table 13. Physical properties and concentrations of inorganic constituents in samples from seeps and surface water in the vicinity 

site, Missouri Continued

-o Site 

< (figs. 1 and 5)

S_ Elvins tailings pile seep

TJ

5 o

~~

8

D)

3

Q.

O

o

3 

0

<D

» *

3

o

3

CO

o SeepG

0

(O

0)

3

O

O 

o

3

CO

<D

1

^ SeepH

§ o

:? SeepK

I

I

CO

0)

Q. Seep 10+07

2

0

i

Date Co, Cu

1 02-23-88 - <10

! 09-26-88 - <10

hi-so-ss - <io

1 03-02-89 - <30

1 05-03-89 - <10

1 09-14-89 -- 10

03-31-93

03-31-93 360 <10

06-24-93 550 <10

203-18-80

303- 18-80

21 1-01-88

l \ 1-06-89 - <20

04-26-90 - <10

06-07-90 - <10

06-07-90 - <10

04-26-90 - <10

06-07-90 - <10

l l 1-07-89 -- <1

04-26-90 - <10

06-07-90 - <10

06-07-90 - <10

03-31-93 - <1

06-24-93 - <10

10-30-93

Cu, Fe

9

10

7

60

5

5

-

5

10 12

8

..

3,500

1,500

25

10

9

250

9

91

7

6,100

<3

29

9

-

Fe, Fe3+

-

_

-

1,200

420

85

..

200

20

-

..

120

-

40

5,200

-

--

Pb 

30

70

70

80

30

67

-

80 

70 

38 

48

80

23

<10

60

<10

20

170

<1

<10

<10

<10

<1

<10

-
Table 13. Physical properties and concentrations of inorganic constituents in samples from seeps and surface water in the vicinity 

site, Missouri Continued

£ Site 

3 (figs. 1 and 5)

(Q 

§ Big River at Bone-hole

o"

(Q

3

Q.

to

0

Cc 

fii.

 ST

2J.

<D 

CO

T1

3 Big River downstream

8

(0

O0

c

3

,_ Mine- A- Joe Creek upstream

to

3

Q.

to 

3 Mine- A- Joe Creek downstream

<

o.

3

v?

CO

O

C

3

S

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<D

3

3

o

c

3.

<g Southwest Creek

(O

o

Date Cot Cu Cut

303- 18-80

!02-24-88 -- <10

to-n-ss -- <io

1 09-27-88 - <10

1 11-30-88 -- <10

1 03-02-89 - <10

^5-04-89 - <10

1 09-14-89 - <10

1 ll-07-89 -- <10

10-26-93 <3 <10 <10

303- 18-80

1 ll-07-89 - <10

10-26-93 <3 <10 <10

203-18-80

04-26-90 - <10

2Q3- 18-80

303-18-80

1 02-24-88 - <10

05-17-88 _ <10

! 09-27-88 - <10

2 1 1-01 -88

1 12-01-88 -- <10

1 03-02-89 - <10

1 05-04-89 ~ <10

! 09-14-89 - <10

04-26-90 ~ <10

Fe

~

<3

<3

10

8

5

8

8

4

24

5

22

9

40

_

8

5

10

20

9

4

4

9

17

Fet Fe3+ Pb 

43

10

<10

20

10

<10

<10

2

2

170 - <10 

30

4

130 - <10 

..

<10

679 - 13 

36

10

<10

10

100

20

<10

<10

18

<10
Table 13. Physical properties and concentrations of inorganic constituents in samples from seeps and surface water in the vicinity 

site, Missouri Continued

-o Site 

«< (figs. 1 and 5)

8^ Elvins tailings pile seep

 o 

3 o

0>

3.

0>

(0

0)

Q.

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0

o

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I

0

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5" 

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3

(0

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= SeepH

0)

3 o

^ SeepK

i

i

(0

0)

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I

o

3

o>

S>

Date

1 02-23-88

J 09-26-88

1 11-30-88

1 03-02-89

J 05-03-89

1 09-14-89

03-31-93

03-31-93

06-24-93

203-18-80

303-18-80

21 1-01 -88

1 11-06-89 

04-26-90

06-07-90

06-07-90

04-26-90

06-07-90

1 11-07-89

04-26-90

06-07-90

06-07-90

03-31-93

06-24-93

10-30-93

Mn Mn, Hg

45

2

5

8

1

<1

..

2 170

3 59

-

5,600 - <0.5

5,300

1,500

65

890

2,600 - .2

780

570

520 - .1

1,300

510

170

79

Hg, Mo Ni Ni, 

<10 510

<10 640

<10 570

<30 430

<10 270

10 350

<0.1 <10 370 400

<.l <10 510 500

-

<20 680

10 70 - 

<10 30

<10 40 -- 

<10 380 - 

<10 440 - 

<1 33 - 

<10 30 - 

<10 20 -- 

<10 10 - 

<10 2

<10 10
Table 13. Physical properties and concentrations of inorganic constituents in samples from seeps and surface water in the vicinity 

site, Missouri Continued

£ Site 

§ (figs. 1 and 5)

(Q 

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(Q

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3

Q.

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Date

303- 18-80

'02-24-88

'05-17-88

'09-27-88

'11-30-88

'03-02-89

'05-04-89

'09-14-89

1 11-07-89

10-26-93

303-18-80

1 11-07-89

10-26-93

^S-IS-SO

04-26-90

Mn Mnt Hg Hgt Mo Ni Nit 

27 - - - <10 <10

92 -- - - <10 <10

49 -- - -- <10 <10

24 - - - <10 <10

34 - -- - <10 <10

54 - - - <10 10

73 .. .. .. 10 10

60 - -- <10 <10

41 61 - <0.10 <10 <10 <10

43 -- <10 <10

40 46 <.10 <10 <10 <10

-

290 - - - <10 <10 -- 

Mine- A- Joe Creek downstream

g

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^03-18-80 

303-18-80 

'02-24-88 

'05-17-88 

'09-27-88 

211-01-88

12-01-88 

03-02-89 

05-04-89 

09-14-89

520

430

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150

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67

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Physical Properties and Concentrations of Inorganic Constituents in Samples from Wells and Piezometers 137
jj Table 13. Physical properties and concentrations of inorganic constituents in samples from seeps and surface water in the vicinity 

00 site, Missouri Continued

£ Site 

| (figs. 1 and 5)

§ Big River at Bone-hole

o"

(Q

0)

3

Q.

15TCD

0

c 

SL

3

0)

^

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5 Big River downstream

o

o.

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3

,_ Mine- A- Joe Creek upstream

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3

Q.

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3 Mine-A-Joe Creek downstream

<

o.

3_

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1

su)

i3

s

w

i

I

to Southwest Creek 

<o

Date Ag

303-18-80

J02-24-88 <1

105-17-88 <1

1 09-27-88 1

1 11-30-88 2

1 03-02-89 <1

! 05-04-89 <1

1 09-14-89 <1

h 1-07-89 <1

10-26-93 <1

303-18-80

1 11-07-89 <1

10-26-93 <1

203-18-80

04-26-90 1

203-18-80

303-18-80

1 02-24-88 <1

105-17-88 <i

1 09-27-88 <1

21 1-01 -88

1 12-01-88 2

1 03-02-89 <1

1 05-04-89 <1

1 09-14-89 2

04-26-90 <1

Agt Sr Tl

-.

34

60

47

34

41

46

66

62

<1 52 <1

62

<1 53 <1

100

_

-

110

'190

160

_.

140

130

170

75

44

V

-

<6

<6

<6

<6

<6

<6

<6

<6

<6

<6

<6

-

<6

_

<6

<6

<6

-

<6

<6

<6

<6

<6

Vt Zn

23

120

98

83

51

55

69

95

100

<1 60

50

150

<1 93

9

63

72

80

250

250

420

390

740

420

220

120

24

i> l Smith and Schumacher (1991).

Data from Missouri Department of Natural Resources, Division of Environmental Quality (written commun., 1980,

3 Data from Missouri Department of Natural Resources, Division of Geology and Land Survey (written commun., 1980)

4 Questionable value.