Effects of abandoned lead and zinc mines and tailings piles on water quality in the Joplin area, Missouri

Barks, J.H. · 1977 · Report

The mining involved bringing the crude ores to the surface where they were milled into lead and zinc concentrates.

This 1977 document, Effects of abandoned lead and zinc mines and tailings piles on water quality in the Joplin area, Missouri, is preserved in the Mountain Man Mining Library for research and reference. Original source: pubs.usgs.gov.

(1,-: hi EFFECTS OF ABANDONED LEAD AND ZINC MINES AND TAILINGS PILES ON WATER QUALITY IN THE JOPLIN AREA, MISSOURI U.S. GEOLOGICAL SURVEY Water-Resources Investigations 77-75 Prepared in cooperation with the Ozark Gateway Council of Governments

BIBLIOGRAPHIC DATA 1. Report No. 3. Recipient's Accession No. SHEET 4. Title and Subtitle 5. Report Dare August 1977 EFFECTS OF ABANDONED LEAD AND ZINC MINES AND TAILINGS PILES ON WATER QUALITY IN THE JOPLIN AREA, MISSOURI 6' 7. 8. Performing Organization Rept. James H. Barks N'USGS/WRI-77-75 9. Performing Organization Name and Address 10. Project/Task/Work Unit No. U.S. Geological Survey, Water Resources Division 1400 Independence Road Mail Stop 200 11. Contract/Grant No. Rolla, Missouri 65401 12. Sponsoring Organization Name and Address 13. Type of Report & Period U.S. Geological Survey, Water Resources Division Covered 1400 Independence Road Mail Stop 200 Final Rolla, Missouri 65401 15. Supplementary Notes Prepared in cooperation with the Ozark Gateway Council of Governments. 16. Abstracts Dissolved zinc concentrations averaged 9,400 pg/L (micrograms per liter) in water from flooded mines and 16,000 ug/L in runoff from tailings areas. Minewater discharges increase dissolved zinc concentrations in receiving streams from a background of about 40 pg/L to about 500 0g/L during periods of low flow. The higher concentrations are sustained during high flow by runoff from the tailings areas. Deposition of tailings on stream bottoms increases zinc concentrations in bottom material from a background of about 100 pg/g (micrograms per gram) to about 2,500 pg/g and increases lead concentrations in bottom material from about 20 pg/g to about 450 pg/g. 17. Key Words and Document Analysis. 17a. Descriptors *Mine drainage, *Mine wastes, *Acid mine water, Mine water, Mines, Metals, Heavy metals, Lead, Zinc, Water pollution, Water quality. 17b. Identifiers/Open-Ended Terms Tri-State District 17c. COSATI Field Group 18. Availability Statement 19. Security Class (This 21. No. of Pages Report) No restriction on distribution UNCLASSIFIED 20. Security Class (This 22. Price Page UNCLASSIFIED USCOMM-DC 8265-P7 FORM NTIS-35 (REV. 10-73, ENDORSED BY ANSI AND UNESCO. THIS FORM MAY BE REPRODUCED

EFFECTS OF ABANDONED LEAD AND ZINC MINES AND TAILINGS PILES ON WATER QUALITY IN THE JOPLIN AREA, MISSOURI by James H. Barks U.S. GEOLOGICAL SURVEY Water-Resources Investigations 77-75 Prepared in cooperation with the Ozark Gateway Council of Governments August 1977

UNITED STATES DEPARTMENT OF THE INTERIOR CECIL D. ANDRUS, Secretary GEOLOGICAL SURVEY V. E. McKelvey, Director For additional information write to: U.S. Geological Survey 1400 Independence Road Mail Stop 200 Rolla, Missouri 65401

CONTENTS Page Abstract Introduction Purpose and scope Mineralization and metal liberation Methodology Ground water Mines Shallow wells Deep wells Surface water Tailings areas Reconnaissance Small area storm runoff Streams Center Creek Turkey Creek Short Creek Summary and conclusions References cited ILLUSTRATIONS Figure 1. Map of the Joplin area, Missouri, showing associated water sampling sites 2. Potentiometric map of the shallow aquifer for September-October 1976 3. Diagrams showing chemical character of water from mines, shallow wells, and deep wells 4. Cross-sectional sketch showing mine-water circulation 5. Profiles of specific conductance, pH,temperature, and dissolved oxygen for mines in ground-water recharge areas and ground-water discharge areas 6. Photograph of tailings piles in the Oronogo-Duenweg mining belt 7. Sketch of 7-acre tailings area storm runoff site 8. Photograph of seepage from large tailings pile at 7-acre storm runoff site 9. Graphs showing dissolved-solids concentrations in storm runoff from 7-acre tailings area, June 23-28, 1976 10. Graphs showing dissolved zinc concentrations in storm runoff from 7-acre tailings area, June 23-28, 1976

ILLUSTRATIONS--continued Page Figure 11. Graphs showing dissolved cadmium and lead concen­ trations in storm runoff from 7-acre tailings area, June 23-28, 1976 12. Graphs showing relation of discharge and specific conductance to distance upstream from the mouth of Center Creek, September 20-22, 1976 13. Graphs showing relation of dissolved zinc concen­ tration and discharge to distance upstream from the mouth of Center Creek, Septemger 20-22, 14. Graphs showing relation of zinc and lead concen­ trations in bottom material and discharge to distance upstream from the mouth of Center Creek, September 20-22, 1976 TABLES Table 1. Generalized section of geologic formation in the Joplin area, Missouri (from Feder and others, 1969) 2. Water-quality data for mines 3. Water-quality data for wells in the shallow aquifer 4. Water-quality data for wells in the deep aquifer 5. Average values of characteristics and dissolved constituents of water from mines, shallow wells and deep wells 6. Physical and hydrologic characteristics of Center, Turkey, and Short Creeks 7. Water-quality reconnaissance data for tailings areas 8. Characteristics and dissolved constituents of water flowing from eight tailings sites and Center Creek, March 1976 9. Water-quality data for storm runoff from 7-acre tailings area 10. Range in concentrations of dissolved metals in storm runoff from 7-acre tailings area, June 23-28, 1976 11. Range in dissolved zinc concentrations in water from Center Creek near Carterville and near Smithfield 12. Water-quality reconnaissance data for streams 13. Seepage-run data for Center Creek, September 1976 14. Seepage-run data for Turkey Creek, September 1976

Effects of Abandoned Lead and Zinc Mines and Tailings Piles on Water Quality in the Joplin Area, Missouri By James H. Barks ABSTRACT Dissolved zinc concentrations averaged 9,400 pg/L (micrograms per liter) in water from abandoned lead and zinc mines, some of which discharge at the surface. Contamination of the shallow aquifer (cherty limestones) by the highly mineralized mine water is limited to the immediate mining area. The quality of water in the deep aquifer (cherty dolomites and sandstone) is generally excellent. Dissolved zinc concentrations averaged 16,000 pgiL in runoff from tailings areas. However, during a summer storm, runoff from a 7-acre tailings area contained maximum dissolved zinc, lead, and cadmium concentra­ tions of 200,000; 400; and 1,400 pg/L, respectively. Mine-water discharges increase dissolved zinc concentrations in receiving streams from a background of about 40 pg/L to about 500 pg/L during periods of low flow. The higher concentrations are sustained during high flow by runoff from the tailings areas. Deposition of tailings on stream bottoms increases zinc concentrations in bottom material from a back­ ground of about 100 pgig (micrograms per gram) to about 2,500 pg/g and increases lead concentrations in bottom material from about 20 pg/g to about 450 pg/g. INTRODUCTION Commercial development of the mineral resources of southwestern Missouri began about 1850 and spread into southeastern Kansas and north­ eastern Oklahoma, forming the Tri-State District with Joplin as the urban center. The value of the Tri-State mineral production from 1850 to 1950 exceeded one billion dollars, and until 1945 the region was the world's leading producer of lead and zinc concentrates, accounting for one-half of the zinc and one-tenth of the lead produced in the United States (Gibson, 1972). By 1950 most of the rich ores had been extracted, and mining and milling operations declined during the 1950's and ceased in the 1960's. Throughout the mining era ground water remained a problem to the district. The natural level of the water table was usually higher than the mines and flooding of the mines was controlled only by constant pumping. When pumpage declined in the 1950's and 1960's the mine drifts and shafts filled with water.

The mining involved bringing the crude ores to the surface where they were milled into lead and zinc concentrates. Barren rock was discarded in piles while the ore-bearing rock was crushed and ground into a fine gravel The minerals were separated from the rock by a jigging process and the tailings were skimmed off and discarded in large piles. In 1976 the U.S. Geological Survey made a study of the effects of the abandoned and flooded mines and tailings piles on water quality in the southwestern Missouri part of the Tri-State District (fig. 1). The study area covers approximately the southwestern quarter of Jasper County, an area of about 280 mil (square miles), and is bounded by long 94°15' W. and the Missouri-Kansas state line, and lat 37°15' N. and the Jasper-Newton County line. Although some mining was done in Newton County, most was done in Jasper County within a few miles of Joplin. In conjunction with the mine-related study, flow characteristics were determined for streams in the Joplin area of southwestern Missouri (Skelton, 1977). The report by Skelton is an update and revision of flow-frequency and flow-duration data from a previous report by Feder and others (1969). For the convenience of readers who may want to use metric units, English units may be converted to metric units using the following conversion factors: English Multiply by Metric acres square kilometers (km2) cubic feet per second (ft3/s) 0.02832 cubic meters per second (m3/s) cubic yards (yd 3) cubic meters (m3) feet (ft) meters (m) inches (in) millimeters (mm) miles (m) square miles (mi ) kilometers (km) square kilometers (km2 ) PURPOSE AND SCOPE The principal objective of this study was to evaluate the extent to which abandoned mines and tailings piles are affecting ground and surface waters in the Joplin area, with emphasis on Center and Turkey Creeks. The approach involved characterizing the quality and determining the movement of mine water, and seepage and runoff from tailings areas. It also involved delineating specific reaches of streams that are affected and, as possible, separating the effects of mine-water discharge from those of tailings area discharge. MINERALIZATION AND METAL LIBERATION Sphalerite (zinc sulfide) and galena (lead sulfide) were the most important minerals in the Joplin area. Other minerals commonly associated with the zinc and lead were pyrite, marcasite, dolomite, calcite, chert, and jasperoid (Feder and others, 1969, p. 10).

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JASPER COUNTY NEWTON COUNTY Cif= fr C) I D 4 MIL ES ZOO 01 U) EXPLANATION 37°00 K ANSAS CITY WATER SAMPLING SITES MISSOURI ST. LOUIS MAP NO. SYMBOL ST REAMS AND TAILINGS DITCHES ABANDONED MINE SHAFTS

Study Area Aquifer Wells 201 - 221 Shallow 1 Deep Aquifer Wells

Figure l.--Map of the Joplin area, Missouri, showing associated water sampling sites.

Degradation of water quality is associated with the removal of these minerals from their reducing environment. Oxidation of insoluble metallicsulfide minerals in the mines and tailings to a soluble form and subsequent solution and hydrolosis of the soluble sulfates produces sulfuric acid and liberates metals. However, neutralization of the acid by calcium carbonate in the rocks ultimately results in high concentrations of calcium, sulfate, and zinc in solution. Because of their insolubility most other metals are rapidly precipitated. METHODOLOGY Samples were collected and analyzed for minerals and gases according to methods described by Brown and others (1970), for organic substances according to Goerlitz and Brown (1972), and for suspended sediment accord­ ing to Guy (1969), and Guy and Norman (1970). Stream discharges were computed from measurements made using a wading rod and current meter follow­ ing procedures outlined in Buchanan and Somers (1969). All analyses were made at U.S. Geological Survey laboratories. Field techniques used in this study are described briefly in the following paragraphs. Wells were pumped several minutes prior to sample collection and whenever possible samples were collected before the water entered a pressure tank. Mine water was collected by lowering a kemmerer style nonmetallic, clear acrylic bottle into the mine shafts and closing the sampler at the desired depth. Depth-integrated water samples were collected at several points in the stream cross-section by lowering bottles to the bottom and raising them to the surface at a constant rate. These samples were composited to represent the entire stream cross-section. Bottom material samples were collected by scooping material from the upper 2 in (inches) of the bottom at several locations in the cross section. The bottom material samples were always collected from reaches with moderate velocities. The composite consisted mainly of very fine to very coarse sand-size particles. Chemical constituents referred to as "dissolved" were determined from samples filtered at the time of sampling through 0.1 pm (micrometer) membrane filters from a polyvinyl chloride chamber using a peristaltic pump as the pressure source (Kennedy and others, 1976). The only exception was the dissolved organic carbon samples which were filtered through 0.45 um silver filters from a stainless steel chamber using compressed nitrogen as the pressure source. Chemical constituents referred to as "total" were determined from unfiltered samples and include amounts recovered from suspended sediment or bottom material by soft digestion procedures. Samples to be analyzed for cations were acidified with double-distilled analytical-grade nitric acid to a pH of less than 3.

Water temperature, specific conductance, pH, alkalinity, and dissolved oxygen were determined in the field. Water temperature was measured with a mercury thermometer to the nearest 0.5°C (degrees Celsius). Specific conductance was measured using a portable conductivity meter with temper­ ature compensation designed to express readings in umhos/cm at 25°C (micromhos per centimeter at 25 degrees Celsius). The potentiometric method was used to measure both the pH and alkalinity. The inflection points in the titration for alkalinity with 0.01639 normal sulfuric acid were 8.3 and 4.5 for bicarbonate. The azide modification of the Winkler method was used for dissolved oxygen determinations. The only departure from these methods was the determination of temperature, specific conductance, dissolved oxygen, and pH profiles in mine shafts using an electronic instrument calibrated according to the manufacturer's instructions. GROUND WATER Important aquifers in the area include the shallow aquifer in cherty limestones of Mississippian age and the deep aquifer in cherty dolomites and sandstone of Ordovician and Cambrian age. The shallow and deep aquifers are separated by relatively impermeable silty limestones and shale of Mississippian and Devonian age. A generalized section of the geologic formations and their hydrologic properties is given in table 1, in the back of the report. The shallow aquifer reaches the surface at places and extends as deep as 500 ft (feet). Brecciated areas generally are highly permeable while surrounding areas of dense limestone have low permeabilities. Mineral deposits in the brecciated areas were mined at depths from 100 to 250 ft. The abandoned mines contain large volumes of highly mineralized water. A potentiometric map of the shallow aquifer (fig. 2) was prepared from water levels that were measured in approximately 200 shallow wells and mine shafts in September and early October 1976 during a period of little precipi­ tation and low streamflow. The map shows the slope and direction of ground­ water movement. Water levels represent the water table except for the few wells and mines that have water under artesian pressure. The water table is usually close to land surface near main streams and from 25 to 100 ft below land surface away from main streams. Center and Turkey Creeks are in hydraulic connection with the shallow aquifer and generally act as drains. Hydrologic divides generally correspond to topographic divides and movement of the ground water is from the divide areas to the streams. Regional movement of the water in the shallow aquifer is toward the west. A comparison of the September-October 1976 and June 1966 (Feder and others, 1969, p. 28) potentiometric maps shows that except for the area north of Duenweg, the altitude of the water table and movement of the ground water is unchanged. In 1966 heavy pumping in the area north of Duenweg formed a cone od depression and altered the ground-water flow pattern causing water to flow into the cone to replace water that had been pumped out. Most of the pumpage stopped soon after the 1966 water-level measure­ ments were made. The 1976 measurements show a recovery of about 100 to 150 ft in water-table altitude in the Duenweg area. Consequently, the 1976

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C/) CO I CD Z CO — 9*0 NEW TON COUNTY JASPER COUNTY 4 MILES EXPLANATION 37°0 0' moo--- POTENTIOMETRIC CONTOUR SHOWS ALTITUDE OF POTENTIOMETRIC SURFACE, DASHED WHERE APPROXIMATELY LOCATED. CONTOUR INTERVAL 50 FEET. DATUM IS MEAN SEA LEVEL. NUMBER IS ALTITUDE OF POTENTIOMETRIC SURFACE IN FEET ABOVE MEAN SEA LEVEL. ( F ) INDICATES A FLOWING WELL. Figure 2.--Potentiometric map of the shallow aquifer for September-October 1976.

map does not show a depression in the water table north of Duenweg. The deep aquifer is reached at a minimum depth of about 300 ft and extends as deep as 1,800 ft. Water in the deep aquifer is under artesian pressure, but water-level measurements indicate that the potentiometric surface of the deep aquifer is below that of the shallow aquifer (Feder and others, 1969, p. 12). This relationship favors downward seepage of water, and where faults, fracture openings, and wells connect the aquifers, water can leak directly from the shallow aquifer to the deep aquifer. Where the aquifers are separated by the Northview Formation, the Chattanooga Shale, or both, these shales act as confining beds permitting little water movement. In 1976 water samples were collected from 14 mines, 21 shallow wells, and 14 deep wells. Results of analyses of these samples are shown in tables 2, 3, and 4, respectively, in the back of the report. The data are summarized in table 5 and figure 3 and discussed under the topics, "Mines," "Shallow wells," and "Deep wells." Mines Dissolved-solids concentrations in water from mine drifts are generally greater than 1,000 mg/L (milligrams per liter). In ground-water recharge areas (higher altitudes away from main streams) downward water movement prevents water in the drifts from circulating up into the mine shafts, and water in these shafts contain less than 500 mg/L dissolved solids. Conversely, in ground-water discharge areas (lower altitudes near main streams or water under artesian pressure) upward water movement causes water in the drifts to circulate up through the mine shafts. This phenomenon is illustrated by the sketch in figure 4 and by specific conductance, pH, temperature, and dissolved oxygen profiles (fig. 5) that represent average characteristics for seven mines (map nos. 101, 102, 103, 106, 107, 108, and 113) in recharge areas and for three mines (map nos. 104, 112, and 114) in discharge areas. Average depth to the water surface was 35 ft in recharge areas and 1 ft in discharge areas. The relation between dissolved solids (DS) and specific conductance (SC) for water in the drifts and shafts is DS=(0.99XSC)-121; the standard error of estimate is 49 mg/L DS. In table 2, in the back of the report, those analyses with dissolved-solids concentrations less than 500 mg/L are for water collected from shafts in ground-water recharge areas. Those with dissolved-solids concentrations greater than 900 mg/L are for water collected from drifts in the recharge areas or from shafts in ground-water discharge areas. All of the analyses were used to compute values shown for mines in table 5 and figure 3. Water in limestone rocks is usually a calcium bicarbonate type, but water in the abandoned mines is a calcium sulfate type (fig. 3), reflecting the sulfide mineralization. Average concentrations of dissolved iron, manganese, cadmium, and zinc in the mine water (table 5) exceed concentrations of 300, 50, 10, and 5,000 pg/L, respectively, recommended as drinking water standards (U.S. Public Health Service, 1962). Concentrations of other metals in the mine water are

Table 5 .--Average values of characteristics and dissolved constituents of water from mines, shallow wells, and deep wells Characteristic or constituent Silica (Si02), in mg/L Calcium (Ca), in mg/L Magnesium (Mg), in mg/L Sodium (Na), in mg/L Potassium (K); in mg/L Bicarbonate (HCO3), in mg/L Sulfate (SO4), in mg/L Chloride (C1), in mg/L Fluoride (F), in mg/L Dissolved solids, in mg/L Hardness as CaCO3, in mg/L--- Alkalinity as CaCO3, in mg/L-- Specif-:: conductance, in prnhos/cm at 25°C pH, in units Temperature, in °C Aluminum (Al), in pg/L Cadmium (Cd), in g/L Chromium (Cr), in pg/L Cobalt (Co), in pg/L Copper (Cu), in pg/L Iron (Fe), in pg/L Lead (Pb), in p.g/L Manganese (Mn), in pg/L Mercury (Hg), in pg/L Nickel (Ni), in g/L Silver (Ag), in pg/L Zinc (Zn), in pg/L Average value Mines Shallow wells Deep wells 1,030 1,160 5,100 9,400 1,100

Ca HCO3 Mg Na+K SO4 Fe Zn MINES Ca HCO3 Mg Na+K SO4 Fe Zn SHALLOW WELLS Ca Mg Na+K HCO3 SO4 Fe Zn DEEP WELLS Figure 3.--Chemical character of water from mines, shallow wells, and deep wells.

Recharge area Discharge area Possibly Drift connected Figure 4.--Cross-sectional sketch showing mine-water circulation. Vertical scale is highly exaggerated.

--- Average for seven mines in ground-water recharge areas Average for three mines in ground-water discharge areas 500 1000 1500 SPECIFIC CONDUCTANCE IN MICROMHOS PER CENTIMETER AT 25 DEGREES CELSIUS 6.5 7.0 7.5 pH, IN UNITS TEMPERATURE, IN DEGREES CELSIUS Shaft DISSOLVED OXYGEN IN MILLIGRAMS PER LITER DIAGRAM OF MINE SHAFT AND DRIFT Figure 5.--Profiles of specific conductance, pH, temperature, and dissolved oxygen for mines in ground-water recharge areas and ground-water discharge areas.

well below the drinking water standards. High concentrations of zinc in the mine water are particularly significant because zinc is highly toxic to aquatic animals and some of the mine water reaches the main streams in the area as discussed later in the report. Shallow Wells Many of the 21 shallow wells that were sampled are located between the flooded mines and Center and Turkey Creeks. Average depth of the wells is 243 ft, which is a little deeper than most mines in the area. Water in the shallow wells is generally a calcium bicarbonate type (fig. 3). Only four of the wells (map nos. 203, 204, 211, and 219) have water with sulfate concentrations greater than 60 mg/L. Three of these are in, or very near, mines and the other is probably in contact with sulfide minerals. One of the wells (map no. 204), known to penetrate a mine, has water-quality characteristics similar to the mine water including a dissolvedsolids concentration of 1,190 mg/L, a sulfate concentration of 560 mg/L, and a zinc concentration of 8,800 pg/L. Water from the other shallow wells is considerably less mineralized than the mine water. Metals concentrations in water from the shallow wells are generally low, except for zinc. Zinc concentrations average 1,100 pg/L and are probably influenced by galvanized plumbing and (or) local sulfide mineral deposits as described by Feder and others, 1969, p. 34. Results of the shallow well sampling indicate that there is not wide­ spread movement of the highly mineralized mine water in the shallow aquifer. Deep Wells Water in the deep aquifer is a calcium magnesium bicarbonate type (fig. 3) and it can be distinguished from water in the shallow aquifer by its lower mineral content and lower calcium magnesium (Ca:Mg) ratio. The average Ca:Mg ratio (calcium and magnesium expressed in milliequivalents) is 23 for water in the mines, 23 for water in the shallow wells, and 1.7 for water in the deep wells. The lower ratio for water in the deep aquifer is indicative of the higher magnesium content of the dolomitic rocks. The Ca:Mg ratios and concentrations of dissolved solids, sulfate, and zinc in water from Webb City Well No. 6 (map no. 305), Webb City Well No. 7 (map no. 308), and Carthage Well No. 1 (map no. 311) indicate mixing with water from the shallow aquifer. The water from the shallow aquifer may be leaking directly into these wells or may be entering the deep aquifer through faults, fracture openings, or wells that connect the aquifers. The Oronogo-Duenweg mining belt extends along the east edge of Webb City. Water from deep wells on the east side of Webb City is more mineralized than water from deep wells on the west side.

In June 1972 the dissolved-solids concentration in water from Webb City Well No. 10 was 840 mg/L. This well is located near the mining belt and the high dissolved-solids content indicates the possibility of mine-water contamination of the deep aquifer on the east side of Webb City. This well has been abandoned as a source of municipal water because of the high mineralization of the water (Raymond Lawrence, Supt. Webb City Water Dept., oral commun., 1976). SURFACE WATER Center Creek, Turkey Creek, and Short Creek drain about 70, 18, and 5 percent of the mining area, respectively. Some physical and hydrologic characteristics of these streams are given in table 6. All three streams flow westward and are characterized by alternating pools and riffles, and mixed sand, gravel, and boulder bottoms. The lower part of Center Creek, the largest of the three streams, flows through the northern part of the mining area and into the Spring River near the Missouri-Kansas state line. Most of the baseflow originates in the headwater area, with little or no increase and some losses in the lower reach (Feder and others, 1969, p. 54). About 1,970 acres of tailings piles having a total volume of approximately 38 million yd 3 (cubic yards), cover the lower part of the basin (Joseph R. Miller, Ozark Gateway Council of Governments, written commun., 1977). Most of these tailings are in the Oronogo-Duenweg mining belt. Discharges from at least three flowing mines enter Center Creek. Turkey Creek, south of and parallel to Center Creek, flows through the northern part of Joplin and into the Spring River in Kansas, just across the state line. It is located in the center of the mining area. Tailings piles are scattered throughout the basin and cover an area of about 600 acres, with a total volume of about 10 million yd 3. The flow and quality of water in Turkey Creek are greatly altered by sewage plant discharge at Joplin, industrial discharges, and mine-water discharge from at least one abandoned mine. Short Creek, south of and parallel to Turkey Creek is a small stream that originates just west of Joplin. After crossing the state line it flows 4.3 mi (miles) in Kansas before entering the Spring River. Although Short Creek has a total drainage area of 18-mi2 (square miles) only about 7.6 mil contribute to the flow at the state line. Mining activities in the upper part of the basin have left about 185 acres (2.9 million yd 3) of tailings piles scattered on the surface. Tailings Areas The distribution and size of tailings piles on the surface generally correspond to the distribution and size of mines beneath the surface. However, some of the ore was removed from the area for processing and some of the tailings have been removed to be used for road surfacing and railroad ballast, or ground into sand for sand blasting. The greatest concentration of tailings

Table 6.--Physical and hydrologic characteristics of Center, Turkey, and Short Creeks Drainage area (mil) Length (mi) Discharge at Missouri-Kansas Stream state line (ft3/s) Total In Missouri Total In Missouri Average 7-day Q101 Center Creek--- Turkey Creek--- Short Creek 7-day Q10 is the 7-day average minimum flow with a recurrence interval of 10 years. 2 7-day Q10 for Turkey Creek is indeterminent because of irregular patterns of stream regulation.

piles is in the Oronogo-Duenweg mining belt (fig. 6), which is about 2 mi wide and 10 mi long, reaching from Oronogo to Duenweg. This mining area is in the Center Creek basin, except for the southwestern edge which is in the Turkey Creek basin. Outside the Oronogo-Duenweg belt the tailings piles are generally scattered and intermixed with woodlands and farmlands. Regardless of the location, runoff and seepage from the tailings piles reach the main streams, either directly or through natural or man-made drainages. Surface drainage to Center Creek from the Oronogo-Duenweg mining belt is primarily by Mineral Branch, located in the center part of the belt (fig 1). It originates southwest of Prosperity and flows into Center Creek at Highway D about 1.5 mi upstream from Oronogo. Another drainage, Stoutt Branch, origi­ nates in the mining belt southeast of Prosperity, but leaves the mining area and runs through farmlands and woodlands before entering Center Creek just downstream from Lakeside. The Sunset mine (map no. 109) and a nearby unnamed mine (map no. 110) discharge about 1 ft3/s of water to Mineral Branch at Carterville during periods of low flow. Otherwise, Mineral Branch is dry upstream from Carterville and Stoutt Branch is dry throughout its length during periods of little or no rainfall, but both carry large volumes of water during periods of heavy rainfall. These two branches are important from the standpoint of the effects of the tailings areas on water quality in Center Creek. Reconnaissance.--During the reconnaissance sampling in March 1976 water flowing at eight tailings sites was collected and analyzed to determine the variation in types and concentrations of major ions and minor elements, as shown in table 7 in the back of the report. The eight tailings sites are scattered throughout the area, but most are located in the Oronogo-Duenweg mining belt. Sources of the water samples vary from seepage directly out of individual tailings piles to flow in ditches draining areas completely covered by tailings, to flow in ditches draining areas that are only partly covered by tailings. Water at two of the sites, Mineral Branch at Carterville and Leadville Hollow near Joplin, is derived in part from mines that discharge at the surface. The samples were collected during a period of moderate rainfall while surface runoff was taking place. In table 8 characteristics and dissolved constituents of water from the tailings areas are compared with those for a March 1976 sample collected from Center Creek upstream from the mining area. Water from the tailings areas is more mineralized than water from Center Creek near Fidelity, and is a calcium sulfate type rather than calcium bicarbonate. The higher sulfate concentrations reflect the oxidation and solution of sulfide minerals still present in the tailings. Chromium, cobalt, mercury, nickel, and silver are present in tailings area water at about the same low concentrations as in water from Center Creek upstream from the mining area. Aluminum, iron, and manganese concentrations are considerably higher in the tailings water, but these metals are gener­ ally nontoxic to aquatic animals. Metals that are toxic to aquatic animals

Figure 6.--Photograph of tailings piles in the Oronogo-Duenweg mining belt.

Table 8.--Characteristics and dissolved constituents of water flowing from eight tailings sites and Center Creek, March 1976 Center Creek near Character Eight tailings sites Fidelity, Mo. or constituent Maximum Minimum Average (one analysis) Calcium (Ca), in mg/L--- Bicarbonate (HCO3), in mg/L Sulfate (SO4), in mg/L Dissolved solids, in mg/L Specific conductance, in phos/cm at 25°C 1,100 pH, in units Aluminum (Al) in pg/L 4,200 Cadmium (Cd), in pg/L Chromium (Cr), in pg/L Cobalt (Co), in pg/L Copper (Cu), in pg/L Iron (Fe), in pg/L Lead (Pb), in pg/L 1,300 in pg/L Mercury (Hg), in pg/L--- Nickel (Ni), in pg/L Silver (Ag), in pg/L Zinc (Zn), in pg/L 35,000 16,000

at low concentrations but occurred in the tailings water at moderate to high concentrations include zinc, lead, copper, and cadmium. Of particular significance are the high concentrations of zinc. Uniformly high zinc concentrations (11,000 to 35,000 ug/L) were in water at all six of the sites where 80 to 100 percent of the flow was considered to be derived from tailings seepage or runoff. Water from the other two sites (map nos. 14 and 28) was derived from predominantly nontailings areas and contained zinc concentrations of less than 2,000 ug/L. The maximum concentration (35,000 ug/L) was in water with the lowest pH (3.5), but the pH of water from other sites with high zinc concentrations ranged from 4.9 to 7.2. Lead concentrations were generally less than 5 wg/L in water with pH values greater than 7.0, but were as high as 1,100 and 1,300 ug/L in the water with pH values of 4.9 and 3.5, respec­ tively. Copper concentrations were less than 16 ug/L except for the acid-water drainage sample (pH 3.5) which had the maximum concentration of 350 ug/L. Cadmium concentrations ranged from 25 to 60 ug/L in water from the six sites where the flow was considered to be mostly tailings seepage and runoff, but were 1 and 3 ug/L at the two sites where only a small part of the flow was derived from tailings areas. In May 1976 specific conductance and pH were determined for 50 water samples collected from tailings seepage and drainage ditches located through­ out the area. Specific conductance ranged from 191 to 1,800 and averaged 588 phos/cm at 25°C and pH ranged from 3.5 to 7.9 and averaged 6.6. These values compare closely with those determined in the eight samples from which other characteristics and dissolved constituents were determined, table 8. The maximum specific conductance was for water in a drainage ditch receiving discharge from a mine and the minimum pH was for seepage directly out of a tailings pile. In samples from 24 open pits and lakes, specific conductance ranged from 177 to 1,800 and averaged 939 umhos/cm at 25°C. Some of this water is highly mineralized because of long exposure to sulfide minerals and calcium carbonate rocks. However, pH values ranged from 3.2 to 8.2 and averaged 7.3, indicating that acid formed by the solution and hydrolosis of the soluble sulfates is neutralized by the calcium carbonate rocks. Only three pH values were less than 7.0. Small area storm runoff.--The area selected for storm runoff sampling (fig. 7) is 7.0 acres in size. The surface is 100 percent tailings, consist­ ing mainly of a large tailings pile, but including parts of three smaller barren rock piles. The proportion and types of material present appear to be representative of that found throughout the mining area. Drainage from the 7-acre site is well defined and enters Stoutt Branch about 200 ft upstream from the reconnaissance site (map no. 8). A continuous-stage recorder and weir were installed at the sampling site (map no. 7) so that runoff from the area could be computed. On June 23, 1976, 5.14 in. of rain fell on the area between 0430 and 1430 h (hours). Antecedent conditions consisted of several days dry weather with no flow at the site.

Drainage boundary r Boulder pile t Thin layer of tailings (5,000 yd 3) t Boulder pile Boulder pile Gage, weir, and sampling site Stoutt Branch Figure 7.--Sketch of 7-acre tailings area storm runoff site (not to scale). Site numbers 7 and 3 refer to those on figure 1.

Runoff at the gage increased from 0 ft3/s (cubic feet per second) at 0430 h to a peak of about 10 ft3/s at 0800 h, then gradually decreased to 0.6 ft3/s at 1200 h. Flow that occurred after 1200 h was mainly seepage out of the large tailings pile (fig. 8). This seepage gradually decreased until it stopped on July 2, about 9 days after the runoff began. Except for light rainfall that occurred on June 24 at 0300 h no additional rain fell between June 23 and July 2. Six samples were collected during the rise, one was collected near the peak, and thirteen samples were collected during the recession, table 9 in the back of the report. The first sample was collected on June 23 at 0540 h, about 30 min (minutes) after runoff started. The concentrations of dissolved inorganic constituents are inversely related to the amount of runoff as indicated by figure 9. The relation between dissolved solids and specific conductance for the storm runoff water is DS-(0.79XSC)-37; the standard error of estimate is 35 mg/L DS. On June 23, dissolved-solids concentrations decreased from 348 mg/L at 0540 h to 38 mg/L at the peak (0755 h), then gradually increased to 392 mg/L at 2140 h. Part of the increase to 664 mg/L on June 24 at 0840 h may be due to flushing caused by the shower that occurred at 0300 h. Dissolved-solids concentrations decreased to 410 and 358 mg/L on June 25 and 28, respectively. Changes in dissolved-solids concentrations reflect changes primarily in concentrations of calcium, zinc, and sulfate. The range in concentrations of metals dissolved in the storm runoff water is given in table 10. Generally, the minimum concentrations occurred during peak runoff and maximum concentrations occurred near the beginning or near the end of runoff. Zinc, cadmium, and lead are particularly signif­ icant because of their high concentrations (fig. 10 and 11), and their high toxicity to aquatic animals. The pH of the storm runoff water ranged from 4.2 near the beginning of runoff to 4.8 near the peak to 3.5 by June 28 when the last sample was collected. Concentrations of metals in the water-suspended sediment mixture (two of the samples) indicate that during storm runoff nearly all of the zinc is in solution, but large amounts of lead, aluminum, and iron are associated with the suspended sediment. Small amounts of cadmium, copper, and other metals are also sorbed to the sediment particles. On June 23 storm runoff samples were collected from Stoutt Branch near Prosperity (map no. 8) at 1115 h, and Mineral Branch at Carterville (map no. 12) at 1330 h (see table 7 in the back of the report). Although the flow had peaked, an estimated 120 ft3/s was still flowing in Stoutt Branch. The dissolved-solids concentration was 74 mg/L and pH of the water was 6.3. Concentrations of dissolved metals were low except zinc (5,000 ug/L) and cadmium (60 ug/L). The flow had also peaked in Mineral Branch but an estimated 400 ft3/s of water was still flowing. The dissolved-solids concen­ tration was 236 mg/L and the pH of the water was 6.7. Concentrations of

Figure 8.--Photograph of seepage from large tailings pile at 7-acre storm runoff site.

Concentration,

(-) L/) LIJ 7.0 cr Discharge 6.0 LLJ CD LIJ LU

-J L.) CO Dissolved solids 3.0 CD (-) 2.0 Cr) 1200 0840 0840 June 23 June 24 June June TIME, IN DAYS AND HOURS Figure 9.--Dissolved-solids concentrations in storm runoff from 7-acre tailings area, June 23-28, 1976.

Table 10.--Range in concentrations of dissolved metals in storm runoff from 7-acre tailings area, June 23-28, 1976 [Results in micrograms per liter] Concentration Minimum Maximum Metal Aluminum (Al) Cadmium (Cd) 1,400 Chromium (Cr) Cobalt (Co) Copper (Cu) Iron (Fe) Lead (Pb) Manganese (Mn) Mercury (Hg) Nickel (Ni) Silver (Ag) 3,800 200,Q00 Zinc (Zn)

CONCENTRAT MILLIGRAMS PL 200,000 on June 24 at 0840 h 70,000 60,000 50,000 40,000 30,000 20,000 10,000 1200 0840 0340 I June June June 23 June 24 TIME, IN DAYS AND HOURS Figure 10.--Dissolved zinc concentrations in storm runoff from 7-acre tailings area, June 23-28, 1976.

CONCENTRATION, —Z1,400 on June 24 al 0840 h ]10.0 FEET PER SECOND LLJ C2G c:C 2.0 Cr) .m1 o ) June 23 June 24 TIME, IN DAYS AND HOURS 1200 0840 0840 June June Figure 11.--Dissolved cadmium and lead concentrations in storm runoff from 7-acre tailings area, June 23-28, 1976.

calcium and sulfate were higher, but concentrations of dissolved metals were about the same as in water from Stoutt Branch. The zinc concentration was 6,000 pg/L, cadmium was 74 pg/L, and other metals concentrations were low. Streams Historical data, data collected from the mines and tailings areas, and seepage-run data can be used to show how the quality of water in Center, Turkey, and Short Creeks is affected by the abandoned mines and tailings piles. Center Creek.--The station, Center Creek near Carterville (map no. 6), is 19 mi upstream from the mouth and is at the upstream edge of the mining area. The station, Center Creek near Smithfield (map no. 21), is about 1 mi upstream from the mouth and is downstream from the mining area. Dissolved zinc concentrations in water samples collected monthly from Center Creek near Carterville and bimonthly from Center Creek near Smithfield during water years 1971 to 1975 are summarized in table 11. A water year is from October 1 to September 30. For example, the 1975 water year is from October 1, 1974 to September 30, 1975. Complete analyses of the samples are published in U.S. Geological Survey open-file reports, "Water Resources Data for Missouri." During water years 1974 and 1975 dissolved zinc concentrations for Center Creek near Carterville were at or near background levels while those for Smithfield were consistently high. During water years 1971 to 1973 average concentrations of dissolved zinc were considerably higher at both sites. The higher concentrations for Carterville were probably caused by pumpage of mine water into Grove Creek prior to 1974. The higher concentrations for Smithfield were probably caused by pumpage of mine water into Grove Creek and additional pumpage of mine water or a greater contribution by discharging mines to Center Creek downstream from Carterville. Concentrations of dis­ solved lead, chromium, and copper were uniformly low at both sites during the 1971 to 1975 water years. Results of analyses of reconnaissance samples collected in March 1976 at the stations Center Creek near Fidelity (map no. 1), and Center Creek near Smithfield (map no. 21), are included in table 12 in the back of the report. Center Creek near Fidelity is 26 mi upstream from the mouth and is upstream from the mining area. Analyses of the reconnaissance samples include metals in solution (dissolved), in the water-suspended sediment mixture (total), and in the bottom material (bottom). Dissolved and total lead concentrations were less than 5 and 30 pg/L, respectively, at both sites, but concentrations of lead in the bottom material increased from 10 pg/g near Fidelity to 350 pg/g near Smithfield. The increases in zinc concen­ trations between Fidelity and Smithfield were 20 to 700 pg/L dissolved, 30 to 800 pg/L total, and 110 to 540 pg/g in the bottom material. Dissolved aluminum, iron, and manganese concentrations were each less than 100 pg/L at both sites. However, concentrations of these metals were 10 to 100 times higher in the total and bottom phases than in the dissolved phase at both sites. Cadmium, chromium, cobalt, copper, mercury, nickel, and silver concentrations were low in the dissolved, total, and bottom phases at both sites, with little or no increase downstream from the mining area.

Table 11—Range in dissolved zinc concentrations in water from Center Creek near Carterville and near Smithfield [Results in micrograms per liter] Carterville Smithfield Water years (map no. 6) (map no. 21) Maximum Minimum Average Maximum Minimum Average 1,200 1,900

Discharge measurements were made at 13 sites on Center Creek and near the mouths of Grove Creek and Mineral Branch during a September 1976 seepage run. Specific conductance, pH, and bicarbonate were measured at each site and water and bottom material samples were collected and analyzed for dis­ solved calcium and sulfate and for zinc and lead in solution, in the watersuspended sediment mixture, and in the bottom material, table 13 in the back of the report. The relation of discharge and specific conductance to distance upstream from the mouth of Center Creek is shown in figure 12. At the time the seep­ age run was made the flow in Center Creek was about twice the 7-day 2-year minimum discharge. Although the discharge measurements were not made during a period of exceptionally low baseflow, they delineate areas where baseflow gains and losses may be expected. Surface inflow between Fidelity and Smithfield included 4.4 ft3/s from Grove Creek, 1.0 ft3/s from Mineral Branch (discharge from the Sunset and a nearby unnamed mine), and an estimated 1.0 ft3/s from the D.C. and E. mine below Oronogo which was not discovered until after the seepage run was completed. Stoutt Branch was dry and appears to flow only during periods of moderate to heavy rainfall. Other increases in discharge are attributed to ground-water inflow and decreases are attrib­ uted to seepage losses from the stream. The loss reach between Highway HH and Lakeside and the one downstream from Oronogo were verified by additional measurements. Specific conductance increased from 305 phos/cm at 25°C near Fidelity to 468 phos/cm at 25°C near Smithfield. The difference is due mainly to sudden increases caused by surface inflow from Grove Creek, Mineral Branch, and the D.C. and E. mine and by ground-water inflow along a short reach upstream from Oronogo. The reach just upstream from Oronogo is in a swampy area and is the only place where mine workings cross Center Creek. The increases in specific conductance were caused mainly by increases in calcium and sulfate that, except for Grove Creek, were accompanied by signi­ ficant increases in dissolved zinc (fig. 13). The results indicate that during base-flow conditions nearly all of the increase in dissolved zinc concentration in Center Creek is caused by mine water discharge from the Sunset and a nearby unnamed mine into Mineral Branch at Carterville that enters Center Creek 1.5 mi upstream from Oronogo, subsurface seepage of mine water into Center Creek about one-fourth mi upstream from Oronogo, and discharge from the D.C. and E. mine that enters Center Creek 0.4 mi down­ stream from Oronogo. During high-flow conditions the high dissolved zinc concentrations are sustained by seepage and runoff from the tailings areas that are discharged mainly through Stoutt and Mineral Branches. Total zinc concentrations were usually about 30 pg/L higher than dissolved concentrations indicating most of the zinc is in solution, but some is associated with suspended sediments. Dissolved and total lead concentrations ranged from 1 to 29 and 5 to 59 pg/L, respectively, with no apparent increase downstream from the mining area. Concentrations of zinc and lead in the bottom material (fig. 14) increased about 25 fold downstream from Stoutt Branch and Mineral Branch, the two streams that drain most of the tailings area between Oronogo and Duenweg.

PER SECOND near at near Smithfield Oronogo Fidelity 600 v) Cf) -J LU LU LU CD LC) Specific conductance HWO= LLJ LU LLJ UCC LLJ LC) F-4 D.C. and E. Mineral Grove Creek 20 mine Branch (4.4 ft3/s) (1.0 ft3/s) (1.0 ft3/s) C.) C) 100 CD MOM (-) (-) LU DISTANCE UPSTREAM FROM MOUTH, IN MILES Figure 12.--Relation of discharge and specific conductance to distance upstream from the mouth of Center Creek, September 20-22, 1976.

near a t near Smithfield Oronogo Fidelity FEET PER SECOND

czc 40 (7) D.C. and E. Mineral mine Branch C—) LLJ LLJ O LLJ CC) 0 D (7) AMS CD MICROGR cz:c F— 1--1 CD 1' DISTANCE UPSTREAM FROM MOUTH, IN MILES Figure 13.--Relation of dissolved zinc concentration and discharge to distance upstream from the mouth of Center Creek, September 20-22, 1976.

near at near Smithfield Oronogo Fidelity PER SECOND LU LU ( )

.., Lu Cd

., :c V) CD Mineral Stoutt Branch Branch Grove Creek Zinc (--0 2000 OG LU

IN MICROGRAMS Lead

DISTANCE UPSTREAM FROM MOUTH, IN MILES Figure 14.--Relation of zinc and lead concentrations in bottom material and discharge to distance upstream from the mouth of Center Creek, September 20-22, 1976. CONCENTRATION IN BOTTOM MATERIAL

The increase appears to be due to the deposition of tailings on the bottom of Center Creek during periods of storm runoff. Turkey creek.--The station, Turkey Creek near Joplin (map no. 29), is about 3 mi upstream from the mouth and is downstream from the mining area. Dissolved zinc concentrations in monthly water samples collected by the U.S. Geological Survey during water years 1971 to 1975 ranged from 60 to 1,260 pg/L and averaged 480 pg/L. The average value appears to be 10 to 20 time higher than the background level. The dissolved zinc concentrations do not appear to be related to discharge, indicating that mine-water discharge causes the high concentrations during low flow and tailings seepage and runoff sustain the high values during high flow, as in Center Creek. Dissolved lead, chromium, and copper concentrations were uniformly low, except for four dissolved copper values in 1972 that ranged from 120 to 190 pg/L, without an apparent reason. The station, Turkey Creek at Duenweg (map no. 22), is about 15 mi upstream from the mouth. Flow in Turkey Creek is intermittent upstream from Duenweg. Results of analyses of reconnaissance samples collected in March 1976 from Turkey Creek at Duenweg and Turkey Creek near Joplin, table 12 in the back of the report, indicate that the entire length of Turkey Creek that has perennial flow is affected by the abandoned mines and tailings piles. Dissolved and total lead concentrations were less than 1 and 30 pg/L, respectively, at both sites, but lead concentrations in the bottom material increased from 40 pg/g at Duenweg to 350 pg/g near Joplin. Dissolved zinc ranged from 240 pg/L at Duenweg to 500 ug/L near Joplin, total zinc ranged from 300 1g/L at Duenweg to 620 pg/L near Joplin, and zinc in the bottom material ranged from 950 Lig/g at Duenweg to 530 pg/g near Joplin. As in Center Creek, dissolved aluminum, iron, and manganese concentrations were 100 pg/L or less at both sites, but concentrations of these metals were several times higher in the total and bottom phases. Concentrations of cadmium, chromium, cobalt, copper, mercury, nickel, and silver were low in the dissolved, total and bottom phases at both sites. Within 2 mi downstream from Duenweg two dams pond water in Turkey Creek, and Great Western Spring flows through a series of ponds and enters Turkey Creek. Because it flows through Joplin, Turkey Creek receives waste discharges from numerous industries and the Joplin sewage treatment plant, as well as urban runoff from Joplin. These numerous alterations and contributions to the natural flow make it difficult and beyond the scope of this study to assess the specific sources of contributions from the mining area. However, a seepage run was made on Turkey Creek in September 1976 to appraise the overall effect of the mining area on the stream. Discharge measurements were made and water and bottom material samples were collected at five sites on Turkey Creek and near the mouths of Joplin Creek and Lone Elm Hollow, table 14 in the back of the report. A rainstorm occurred just before Joplin Creek was sampled causing urban runoff in Joplin Creek. At the time the seepage run was made the Crackerjack mine (map no. 104) was discharging about 0.5 ft3/s into Turkey Creek through Leadville Hollow.

Zinc concentrations in samples from the five sites on Turkey Creek averaged 200 ug/L dissolved, 300 ug/L total, and 2,300 pg/g in the bottom material. Lead concentrations averaged 14 ug/L dissolved, 17 pg/L total, and 230 pg/g in the bottom material. Zinc concentrations in the dissolved, total, and bottom phases and lead concentrations in the bottom phase were uniformly high at each of the sites, confirming that all of Turkey Creek that has perennial flow is affected by the mining area. Zinc concentrations in all three phases and lead concentrations in the bottom phase were also high in Joplin Creek and Lone Elm Hollow and are probably high in other small tributaries to Turkey Creek. Total concentrations of lead and zinc in Joplin Creek were about five times higher than dissolved concentrations, reflecting the large amount of suspended sediment, including fine tailings, that was in the storm runoff. Significant amounts of tailings were present in the bottom material at all seven sites, which accounts for the high concentrations of lead and zinc in the bottom materials at all seven sites. Short creek.--Because of its small size and the fact that only the upper part of it is located in the study area, only one sample was collected from Short Creek. The sample was collected at the Missouri-Kansas state line when the flow was 37 ft3/s, about 6 times the average. Results, table 12 in the back of the report, show a low pH (5.9), a high sulfate concentration (120 pg/L), and a high dissolved zinc concentration (1,600 pg/L). A pollution survey was made by the Missouri Clean Water Commission during a low-flow period in July 1969. Water in Short Creek was flowing 0.7 ft3/s at the state line and had a pH of 3.4, a sulfate concentration of 2,500 pg/L, and a dissolved zinc concentration of 32,000 pg/L (John C. Ford, Missouri Clean Water Commission, written commun., 1977). Other dissolved metal concentrations included 330 pg/L cadmium, 130 pg/L chromium, 90 pg/L copper, 40 pg/L lead, 6,400 pg/L manganese, 650 pg/L nickel, and 10 pg/L silver. The water also had high concentrations of phosphate and fluoride. The extreme values in Short Creek appear to be caused by a combination of mine-water seepage and seepage from a 40-acre gypsum pile on which effluent from a phosphate fertilizer industry is discharged. The effluent has a low pH and very high concentrations of sulfate, fluoride, phosphorus, and metals (Peter L. Smith, Ozark Gateway Council of Governments, written commun., 1977). Because, in the low-flow sample, the pH is lower and the sulfate and metals concentrations are much higher than those in the mine water, it appears that the extreme values are caused mainly by seepage from the large gypsum pile. However, additional sampling would be required to separate the effects of abandoned mines and tailings piles in the Short Creek basin from the effects of seepage from the gypsum pile. SUMMARY AND CONCLUSIONS Mine water in the Joplin area has high average concentrations of dis­ solved calcium (264 mg/L), sulfate (580 mg/L), and zinc (9,400 pg/L). Concentrations of other metals in the mine water are generally low because of the neutralizing effect of calcium carbonate in the rocks. Although wells located in or very near mines may be seriously affected by the mine

water, there does not appear to be widespread dispersion of the highly mineral­ ized mine water in the cherty limestones of the shallow aquifer. The deep aquifer, composed of cherty dolomites and sandstone, is separated from the shallow aquifer by confining beds, but faults, fracture openings, or poorly constructed wells can connect the aquifers resulting in downward leakage. The only places where there is evidence that this may be happening, however, is in the Webb City and Carthage areas. In general, quality of water in the deep aquifer is excellent, but an insufficient number of deep wells are available to completely evaluate the quality of water beneath the mines. Runoff from tailings areas has high average concentrations of dissolved calcium (95 mg/L), sulfate 230 mg/L), and zinc (16,000 pg/L). Runoff from a few tailings piles has a low pH and, consequently, high concentrations of dissolved cadmium, copper, and lead. However, these metals precipitate rapidly after mixing with high pH water, which usually occurs very near the source. The significant effects of the abandoned mines and tailings areas on Center and Turkey Creeks appear to be about a 10-fold increase in dissolved zinc and a 25-fold increase in zinc and lead in the bottom material. Based primarily upon analyses of samples collected from Center Creek upstream from the mining area, background concentrations appear to be about 40 pg/L dissol­ ved zinc, 100 pg/g zinc in the bottom material, and 20 pg/g lead in the bottom material. During low flow the increase in dissolved zinc concentrations in Center Creek are caused mainly by discharges from the Sunset and a nearby mine that enter Center Creek through Mineral Branch 1.5 mi upstream from Oronogo, sub­ surface seepage of mine water into Center Creek about one-fourth mile upstream from Oronogo, and discharge from the D.C. and E. mine that enters Center Creek 0.4 mi downstream from Oronogo. The high dissolved zinc concentrations are sustained during high flow by runoff from the tailings areas that is discharged mainly through Stoutt and Mineral Branches. High zinc and lead concentrations in the bottom material are caused by deposition of tailings on the stream bottom, particularly downstream from Stoutt and Mineral Branches. The numerous alterations and contributions to the natural flow in Turkey Creek make it difficult and beyond the scope of this study to assess the specific sources of contributions from the mining area. However, reconnais­ sance and seepage-run data show that all of Turkey Creek that has perennial flow (downstream from Duenweg) has high concentrations of dissolved zinc and zinc and lead in the bottom material. As in Center Creek, the high dissolved zinc concentrations are caused by mine-water discharge and seepage during low flow and are sustained by tailings area runoff during high flow. The Cracker­ jack mine discharges water to Turkey Creek through Leadville Hollow. Tailings are mixed with the bottom material downstream from Duenweg where flow is perennial. Some of the tailings are washed directly into the stream, but most are transported through Joplin Creek and the numerous small ditches that enter Turkey Creek.

REFERENCES CITED Brown, Eugene, Skougstad, M. W., and Fishman, M. J., 1970, Methods for collection and analysis of water samples for dissolved minerals and gases: U,S. Geol. Survey Techniques Water-Resources Inv., book 5, chap. Al, 160 p. Buchanan, T. J., and Somers, W. P., 1969, Discharge measurements at gaging stations: U.S. Geol. Survey Techniques Water-Resources Inv., book 3, chap. A8, 65 p. Feder, G. L., Skelton, John, Jeffery, H. G., and Harvey, E. J., 1969, Water resources of the Joplin area, Missouri: Missouri Geol. Survey and Water Resources, Water Resources Rept. 24, 97 p. Gibson, A. M., 1972, Wilderness bonanza: Norman, Okla., Univ. of Oklahoma Press, 362 p. Goerlitz, D. F., and Brown, Eugene, 1972, Methods for analysis of organic substances in water: U.S. Geol. Survey Techniques Water-Resources Inv., book 5, chap. A3, 40 p. Guy, H. P., 1969, Laboratory theory and methods for sediment analysis: U.S. Geol. Survey Techniques Water-Resources Inv., book 3, chap. Cl, 52 p. Guy, H. P., and Norman, V. W., 1970, Field methods for measurement of fluvial sediment: U.S. Geol. Survey Techniques Water-Resources Inv., book 3, chap. C2, 59 p. Kennedy, V. C., Jenne, E. A., and Burchard, J. M., 1976, Backflushing filters for field processing of water samples prior to trace-element analyses: U.S. Geol. Survey Open-file Report 76-126, 12 p. Skelton, John, 1977, Streamflow characteristics of the Joplin area, Missouri: U.S. Geol. Survey Open-file Report 77-605, 44 p. U.S. Public Health Service, 1962, Drinking water standards, revised: U.S. Public Health Service Pub. 956, 61 p.

Table 1.--Generalized section of geologic formations in the Joplin area, Missouri (from Feder and others, 1969) [The stratigraphic nomenclature generally follows that of the U.S. Geological Survey and the Missouri Geological Survey; however, there are some variations from the current usage of the U.S. Geological Survey.] cn cn ,r) w O Stratigraphic Unit Thickness Feet Physical Character Depth to Top of Formation, Feet Water-bearing Character i Alluvium Unconsolidated silt, sand, and gravel Outcrop Yields small supplies for domestic and stock use li1 ' tc 0 ri . PENNSYLVANI AN Chesterlan Desmoinesian C cherokee 0-100+ Shales and sandstones with beds of coal Carterville Limestones, shales, Formation and siltstones; generally found filling depressions in underlying rocks Warsaw Dense limestone with Formation some chert Outcrop wells Yields little water to shallow dug Outcrop to 50 Does not yield water to wells Outcrop to 150 Yields little water except in isolated solution channels E

Burlington and Keokuk Limestones Dense cherty limestone, sometimes mineralized with zinc and lead Outcrop to 300 Yields little water where massive, but can yield over 100 gpm in brecciated areas. Solution channels may yield large supplies Generally yields adequate supply for domestic and stock use, rarely over 50 gpm. Supplies many springs Generally yields adequate domestic Deep Aq u ifer Sha l low Aq u ifer Outcrop to 450 Elsey 30+ Fine-grained, very E

Formation cherty limestone; Z7) sometimes all chert cr) and mineralized with N co o zinc and lead Outcrop to 500 Reeds Spring Dark, very cherty, or stock supply. Supplies many argillaceous limeFormation springs mineralized with zinc and lead stone; sometimes Pierson Cherty dolomitic Yields very small quantities of water Formation limestone in upper portion; silty dolomite in lower portion Northview Shale or shaly lime125-625 Confining bed Formation stone; absent in parts of the area

o Compton Shaly limestone Generally does not yield water Formation -,: Bachelor Sandstone Does not yield water to wells Formation Chattanooga Fissile, black, Confining bed Z Shale carbonaceous shale; absent throughout most of area LA Cotter 200+ Cherty dolomite; Yields small quantities of water Dolomite some sandstone beds Jefferson City not Cherty dolomite Yields small quantities of water Dolomite Upp er Low er Roubidoux Cherry dolomite 550-1,000 Generally yields good supply of 9: Formation and several water; most supplies between 50-150 sandstone beds gpm rz Gasconade 300+ Cherty limestone 700-1,150 Yields small supplies of water Dolomite and dolomite; sandstone bed at bottom of formation Eminence and 200+ Dolomite with drusy chert 1,000-1,450 Generally yields good supply of water, especially from lower portion; in lower 50 feet Potosi Dolomites between 50-400 gpm PR EC AM BRI AN CAM BRIAN Derby-Doerun, Davis and Silty dolomites; some siltstones and shales 1,200-1,650 Yields small quantities of water Bonneterre Formations undifferentiated Lamotte Sandstone Quartzose sandstone 1,350-1,750 Yields vary considerably. Formation may be absent over Precambrian highs Granites and rhyolites 1,350-1,850 Generally does not yield water

Table 2.--Water-quality data for mines TOTAL DEPTH DEPTH DISDIS­ DEPTH TO TO DISSOLVED SOLVED OF WATER SAMPLE DISSOLVED MAODTSPO­ MAP SURFACE COLLECTION SOLVED CALNESOLVED TASBICAR­ DATE HOLE OF (FT. (FT. (FT. SILICA CIUM SIUm SODIUM STATION NUMBER NUMBER MINE NAME SIUm BONATE SAMPLE BELOW BELOW BELOW (5102) (CA) (MG) (NA) (K) (HCO3) LSD) LSD) LSD) (mG/L) (MG/L) (MG/L) (Mr,/L) (MG/L) (MG/LI 370516094245501 ST. REGIS 370519094251601 KING WILLIAM 370527094340901 GIBSON 370613094323801 CRACKERJACK 370623094244501 VOGEY 370650094255801 NOWATA 370716094255801 FLORINE 370752094261501 MCGREGOR 370850094270701 SUNSET 370851094265701 UNNAMED -­ 370925094274001 ICE PLANT 7'.3 370941094265501 RHEA 371009094282601 STAR 43 .P )72 371038094282701 UNITY DISDISSPEDIS- DIS- SOLVED SOLVED NONCIFIC DATE OF SAMPLE DIS- SOLVED SOLVED SOLIDS SOLIDS SOLVED CHLOFLUO- (RESI- (SUM OF SULFATE RIDE RIDE DUE AT CONSTI- (504) (CL) (F) 180 C) TUENTS) (MG/L) (MG/L) (MG/L) (MG/L) (MG/L) HARDNESS (CA.mG) (mG/L) CAR- ALKA- CONBONATE LINITY DUCTHARDAS ANCE NESS CAC03 (MICRO- (mG/L) (MG/L) MHOS) PH (UNITS) TEMPERATURE (DEG C) DISSOLVED OXYGEN (MG/L) PERCENT SATURATION ,1 DISSOLVED SOLVED SOLVED DIS- DIS- DIS- DIS- SOLVED DIS- DIS- DIS- DISDATE CARBON ALUM- CAD- CHRO- SOLVED SOLVED SOLVED SOLVED DISDISDISMANSOLVED SOLVED SOLVED SOLVED OF DIOXIDE INUM MIUM MIUM COBALT COPPER IRON ZINC LEAD GANESE MERCURY NICKEL SILVER SAMPLE (CO2) (AL) (CD) (CR) (CO) (CU) (FE) (ZN) (PB) (NN) (HG) (NT) (AG) (MG/L) (UG/L) (UG/L) (UG/L) (UG/L) (UG/L) (UG/L) (UG/L) (u0/L1 (uG/L) (UG/L) (UG/L)

Table 3.--Water-quality data for wells in the shallow aquifer DISDISSTATION NUMBER MAP NUMBER DATE OF SAMPLE OF WELL (FT) DEPTH TOTAL DISSOLVED SILICA (S102) (MG/L1 DISSOLVED CALCIUM (CA) (MG/L) SOLVED HAG NESIUM (XL) SOLVED SODIUM (NA) (MG/L) DISSOLVED POTASS/Um (K) (MG/L) 81cAR80NATE : t3 DISSOLVED SULFATE SOLVED CHLO­ (CL) RIDE (MG/L) SOLVED E11 FLUORIDE (F) (MG/L) ' SOLVED IDS (RESI- ?(i/ T) SOLVED SOLIDS (SUM OF 370316094275301 370438094345201 370500094254801 370535094251301 370620094353301 6g 11176'80 111 %

370628094300501 370645094230801 370659094324501 370735094252801 370829094230701 370834094330401 370841094291401 370841094355001 370853094251501 370953094303501 370958094261101 371006094293401 371016094273601 371033094305201 371100094234401 371114094290601 SPEDISDISDISSOLVED SOLVED DIS- DIS- DOS- SOLVED DIS- DOSNONCIFIC CAR- ALKA- CONCAD- SOLVED SOLVED SOLVED MAN- SOLVED SOLVED ALUMDATE HARD- BONATE LINITY DUCTPH TEMPER- INUM mIum COPPER IRON LEAD GANESE NICKEL ZINC OF NESS HARD- AS ANCE (FE) (PB) (MN) INI) (ZN) SAMPLE (CA.M0) NESS CAC03 (MICROATURE (AL) (CD) (CU) C) (UG/L) (UG/L) (UG/L) (UG/LI (UG/L) (UG/L) (UG/L) (UG/L1 (MG/L) (KG/L) (MG/L1 MHOS) (UNITS) (DEG s o

Table 4.--Water-quality data for wells in the deep aquifer DISDISDISDISDOSSOLVED SOLVED DIS- DIS- SOLVED SOLVED TOTAL DIS- SOLVED MAD- DIS- P0DIS- SOLVED SOLVED SOLIDS SOLIDS DATE DEPTH SOLVED CALNESOLVED TASBIcARMAP OF OF SOLVED CHLOFLUO- (RESI- (SUM OF SILICA CIUM SIUm SODIUM STUN BONATE SULFATE STATION NUMBER NUMBER SAMPLE WELL (SI02) RIDE RIDE DUE AT OONSTI- (CA) (MG) (NA) (K) (HCO3( (504) (CL) (F) 180 C) TUENTs) (FT) (MG/L) (MG/L) (MG/L) (MG/L) (MG/L) (MG/L1 (men) (mG/L) (MG/L) (MG/L) (14G/L) 370416094305201 76-09-08 990 3.2 1.9 160 15 370433094245501 .2 145 160 76-09-08 1228 370532094230501 76-09-08 1402 370818094284501 76-09-09 1475 370827094273901 76-09-07 1015 370842094283301 76-09-09 930 3.6 2.0 160 17 370850094221101 .3 128 160 76-09-08 1473 370852094273001 76-09-07 1415 370911094282901 76-09-09 1500 370956094322901 76-09-08 1400 371030094175901 76-09-08 1250 371040094335601 76-09-08 900 371120094283101 76-09-07 1335 37.1120094283201 76-09-07 925 SPENONCIFIC DISDISDISCARALKACONSOLVED SOLVED DISDISDOSSOLVED DISDISDATE HARD- BONATE LINITY DUCTALUMCADSOLVED SOLVED SOLVED MAN- ,OLvED SOLVED OF NESS HARD- AS ANCE PH TEMPER- INuM MIUM COPPER IRON LEAD GANESE NICKEL ZINC SAMPLI ,cA,m6) (MG/L) NESS (MG/L) (mG/L) (MICROMHOS) (UNITS) ATURE (DEG Cl (AL) (o6/L1 (CD) (Cu) (FE) (fag) (MN) (NI) (ZN) (UG/L) (UG/L) (Uo/L) (uG/L) (uG/L) (UG/L) (us/L1

Table 7.--Water-quality reconnaissance data for tailings areas DIS- DIS- DIS... DIS- DIS- SOLVED SOLVED DIS' DIS... SOLVED SOLVED INSTAN- DIS- SOLVED MAG- DIS- PO- DIS- SOLVED SOLVED SOLIDS SOLIDS TANEOUS SOLVED CAL- NE- SOLVED TAS- BICAR- SOLVED CHLO- FLUO- (PESI- (SUM OF DIS- SILICA CIUM SLUM SODIUM SIUm BONATE SULFATE RIDE RIDE DUE AT CONSTI CHARGE (SI02) (CA) (MG) (NA) (K) (HCO3) (SO4) (CL) (F) 180 C) TUENTS) DATE (CFS) (MG/L) (MG/L) (MG/L) (MG/L) (MG/L) (MG/L) (MG/L) (MG/L) (MG/L) (MG/L) (MG/L) 07186406 - STOUTT BRANCH NEAR PROSPERITY, MO - MAP NUMBER 8 MAR , 1976 JUN MINERAL BRANCH AT PROSPERITY, MO- MAP NUMBER 11 MAR , 1976 MINERAL BRANCH AT CARTERVILLE, MO- MAP NUMBER 12 MAR 1 1976 JUN MAR 0 1976 MAR , 1976 TAILINGS DITCH AT ORONOGO, MO- MAP NUMBER 14 e5 TAILINGS SEEPAGE NEAR ORONOGO, MO -MAP NUMBER 16 07186440 - TAILINGS DITCH NEAR WEBB CITY, MO - MAP NUMBER 17 LEADVILLE HOLLOW NEAR JOPLIN, MO- MAP NUMBER 28 MAR 0 1976 09.o. MAR 0 1976 07187520 - GORDON HOLLOW NEAR JOPLIN, MO- MAP NUMBER 31 MAR , 1976

Table 7.--Water-quality reconnaissance data for tailings areas--Continued SPE..' CIFIC DIS... DIS. CAR... ALKA... CON- PER- SOLVED SOLVED HARD- BONATE LINITY DUCT- DIS... CENT CARBON ALUM... CAD... NESS HARD.. AS ANCE PH TEMPER... SOLVED SATUR- DIOXIDE INUM MIUM (CA,MG) NESS CAC03 (MICRO- ATURE OXYGEN ATION (CO2) (AL) (CD) DATE (MG/L) (MG/L) (MG/L) MHOS) (UNITS) (DEG C) (MG/L) (MG/L) (UG/L) (UG/L) STOUTT BRANCH NEAR PROSPERITY, MO - MAP NUMBER 8 MAR 1976 10oo. JUN 23.o. MINERAL BRANCH AT PROSPERITY, MO- MAP NUMBER 11 MAR 1976 MINERAL BRANCH AT CARTERVILLE, MO- MAP NUMBER 12 MAR 1976 JUN TAILINGS DITCH AT ORONOGO, MO - MAP NUMBER 14 MAR 1976 07186432 - TAILINGS SEEPAGE NEAR ORONOGO MO - MAP NUMBER 16 MAR , 1976 TAILINGS DITCH NEAR WEBB CITY, MO - MAP NUMBER 17 MAR 1976 10.o. LEADVILLE HOLLOW NEAR JOPLIN, MO - MAP NUMBER 28 MAR 1976 GORDON HOLLOW NEAR JOPLIN, MO - MAP NUMBER 31 MAR 1976

Table 7.--Water-quality reconnaissance data for tailings areas--Continued DIS. DIS— SOLVED DIS... DIS— DIS— DIS— SOLVED DIS DIS— DIS— CHRO.. SOLVED SOLVED SOLVED SOLVED MAN— SOLVED SOLVED SOLVED SOLVED TOTAL MIUM COBALT COPPER IRON LEAD GANESE MERCURY NICKEL SILVER ZINC ZINC (CR) (CO) (CU) (FE) (PB) (MN) (HG) (NI) (AG) (ZN) (ZN) DATE (UG/L) (UG/L) (UG/L) (UG/L) (UG/L) (UG/L) (UG/L) (UG/L) (UG/L) (UG/L) (UG/L) STOUTT BRANCH NEAR PROSPERITY. MO - MAP NUMBER 8 MAR , 1976 JUN 07186416 — MINERAL BRANCH AT PROSPERITY, MO- MAP NUMBER 11 MAR 1976 MINERAL BRANCH AT CARTERVILLE, MO - MAP NUMBER 12 MAR 1976 JUN TAILINGS DITCH AT ORONOGO, MO-MAP NUMBER 14 MAR 1976 TAILINGS SEEPAGE NEAR ORONOGO, MO - MAP NUMBER 16 MAR t 1976 MAR t 1976 MAR 1976 07186440 -. TAILINGS DITCH NEAR WEBB CITY, MO - MAP NUMBER 17 LEADVILLE HOLLOW NEAR JOPLIN, MO - MAP NUMBER 28 GORDON HOLLOW NEAR JOPLIN. MO - MAP NUMBER 31 MAR 1976

Table 9.--Water-quality data for storm runoff from 7-acre tailings area 07186405 - TAILING AREA STORM RUNOFF - MAP NUMBER 7 DISDISDISDISSOLVED SOLVED DISDISSOLVED INSTAN- DIS- SOLVED MAG- DIS- PONS- SOLVED SOLVED SOLIDS TANEOUS SOLVED CAL- NE- SOLVED TAS- BICAR- SOLVED CHLO- FLUD- (RESI015SILICA CIUM SIUM SODIUM SIUM BONATE SULFATE RIDE RIDE DUE AT DATE TIME CHARGE (CFS) (S102) (MG/L) (CA) (MG/L) (MG) (MG/L) (NA) (MG/L) (K) (MG/L) (HCO3) (MG/L) (SO4)

(CL) (MG/L) (F) (MG/L) 180 C) (MG/L) JUN 23.o. A4 DISSPEDISSOLVED NONCIFIC SOLSOLIDS CARTOTAL TOTAL ALKACONPERVED (SUM OF HARDBONATE ACIDITY ACIDITY LINITY DUCTDISCENT ORGANIC CONSTI- NESS HARD- AS AS AS ANCE PH TEMPER- SOLVED SATUR- CARBON TUENTS) (CA,MG) NESS H. CAC03 CAC03 (MICROATuRE OXYGEN ATION (C) DATE (MG/L) (MG/L) (MG/L) (MG/L) (MG/L) (MG/L) MHOS) (UNITS) (DEG C) (MG/L) (MG/L) JUN

Table 9.--Water quality data for storm runoff from 7-acre tailings area--Continued 07186405 - TAILING AREA STORM RUNOFF - MAP NUMBER 7 DIS.. DISDISDISSOLVED SOLVED SOLVED DIS- DIS- 015 DIS- SOLVED DIS' DIS DIS- DIS­ ALUM- CAD- CHRO- SOLVED SOLVED SOLVED SOLVED MAN- SOLVED SOLVED SOLVED SOLVED INUM MIUM MIUM COBALT COPPER IRON LEAD GANESE MERCURY NICKEL SILVER ZINC (AL) (CD) (CR) (CO) (CU) (FE) (PB) (MN) (HG) (NI) (AG) (ZN) DATE (UG/L) (UG/L) (UG/L) (UG/L) (UG/L) (UG/L) (UG/L) (UG/L) (UG/L) (UG/L) (UG/L) (UG/L) JUN 23.o. 23.o. 23e.. TOTAL TOTAL TOTAL TOTAL ALUM- CAD- CHRO- TOTAL TOTAL TOTAL TOTAL MAN- TOTAL TOTAL TOTAL TOTAL INUM MIUM MIUM COBALT COPPER IRON LEAD GANESE MERCURY NICKEL SILVER ZINC (AL) (CD) (CR) (CO) (CU) (FE) (PB) (MN) (HG) (NI) (AG) (ZN) DATE (UG/L) (UG/L) (UG/L) (UG/L) ((1G/L) (UG/L) (UG/L) (UG/L) (UG/L) (UG/L) (UG/L) (UG/L) JUN 23.e. b '".

Table 12.--Water-quality reconnaissance data for streams INSTAN- DIS- TANEOUS SOLVED DIS- SILICA CHARGE (S102) DATE (CFS) (MG/L) DIS- DIS- DIS- SOLVED SOLVED SOLVED MAG- DIS- PO- DIS- CAL- NE- SOLVED TAS- BICAR- SOLVED CIUM SIuM SODIUM SIUm BONATE SULFATE (CA) (MG) (NA) (K) (HCO3) (504) (MG/L) (MG/L) (MG/L) (MG/L) (mG/L) (MG/L) 07186200 - CENTER CREEK NEAR FIDELITY, MO - MAP NUMPER 1 07186480 - CENTER CREEK NEAR SMITHFIELD, MO.- MAP NUMBER 21 MAR , 1976 DIS- DIS- DIS- DIS- SOLVED SOLVED SOLVED SOLVED SOLIDS SOLIDS CHLO- FLUO- (RESI- (SUM OF RIDE RIDE DUE AT CONSTI- (CL) (F) 180 C) TUENTS) (mG/L) (MG/L) (MG/L) (MG/L) MAR 1976 MAR 1976 07186485 - TURKEY CREEK AT DUENWEG. MO - MAP NUMBER 22 07186600 - TURKEY CREEK NEAR JOPLIN, MO - MAP NUMBER 29 MAR , 1976

MAR 1976 07186650 - SHORT CREEK AT MO-KANS STATE LINE- MAP NUMBER 30 SPE- NON- CIFIC CAR- ALKA- CON- HARD- BONATE LINITY DUCT- NESS HARD- AS ANCE (CA,MG) NESS cAC03 (MICRO- DATE (MG/L) (MG/L) (mG/L) MHOS) DIS- PER- SUS- SOLVED TOTAL DIS- CENT CARBON PENDFD ALUM- ALUM- PH TEMPER- SOLVED SATUR- DIOXIDE SEDI- INUM INUM ATURE OXYGEN ATION (CO2) MENT (AL) (AL) (UNITS) (DEG C) (MG/L) (M0/L) (MG/L) (UG/L) (UG/L) 07186200 - CENTER CREEK NEAR FIDELITY, MO - MAP NUMBER 1 MAR , 1976 07186480 - CENTER CREEK NEAR SMITHFIELD, m0.- MAP NUMBER 21 MAR , 1976 07186485 - TURKEY CREEK AT DUENWEG, MO - MAP NUMBER 22 MAR 1976 07186600 - TURKEY CREEK NEAR JOPLIN, MO - MAP NUMBER 29 MAR , 1976 MAR , 1976 07186650 - SHORT CREEK AT MO-KANS STATE LINE- MAP NUMBER 30

Table 12.--Water-quality reconnaissance data for streams--Continued TOTAL TOTAL TOTAL TOTAL ALUMIDISCADMIUM DISCHROCOBALT NUM IN SOLVED TOTAL IN SOLVED TOTAL MIUM IN DISIN DISBOTTOM CAD- CAD- BOTTOM CHRO- CHRO- BOTTOM SOLVED TOTAL BOTTOM SOLVED TOTAL MAMIUM MIUM MA- MIUM MIUM MA- COBALT COBALT MA- COPPER COPPER TERIAL (CD) (CD) TERIAL (CR) (CR) TERIAL (CO) (CO) TERIAL (CU) (CU) DATE (UG/G) (UG/L) (UG/L) (UG/G) (UG/L) (UG/L) (UG/G) (UG/L) (UG/L) (uG/G) (UG/L) (UG/L) 07186200 - CENTER CREEK NEAR FIDELITY, MO - MAP NUMBER 1 MAR <10 <10 <10 <10 07186480 - CENTER CREEK NEAR SMITHFIELD, MO. - MAP NUMBER 21 MAR <10 07186485 - TURKEY CREEK AT DUENWEG, MO - MAP NUMBER 22 MAR <10 <10 <10 07186600 - TURKEY CREEK NEAR JOPLIN, MO- MAP NUMBER 29 MAR , 1976 <10 <10 071m6650 - SHORT CREEK AT MO-KANS STATE LINE - MAP NUMBER 30 MAR TOTAL TOTAL TOTAL TOTAL COPPER IRON LEAD DISMANGAIN DISIN DISIN SOLVED TOTAL NESE IN DISBOTTOM SOLVED TOTAL BOTTOM SOLVED TOTAL BOTTOM MAN- MAN- BOTTOM SOLVED MAIRON IRON MA- LEAD LEAD MA- GANESE GANESE MA- MERCURY TERIAL (FE) (FE) TERIAL (PB) (PB) TERIAL (MN) (MN) TERIAL (HG) DATE (UG/G) (UG/L) (UG/L) (UG/G) (UG/L) (UG/L) (UG/G) (UG/L) (UG/L) (UG/G) (UG/L) 07186200 - CENTER CREEK NEAR FIDELITY. MO - MAP NUMBER 1 MAR <10 <10 07186480 - CENTER CREEK NEAR SMITHFIELD, MO. - MAP NUMBER 21 MAR <10 0 7186485 - TURKEY CREEK AT OUFNWEG, MO - MAP NUMBER 22 MAR , 1976 <10 07186600 - TURKEY CREEK NEAR JOPLIN, MO- MAP NUMBER 29 MAR . 1976 07186650 - SHORT CREEK AT MO-KANS STATE LINE - MAP NUMBER 30 MAR , 1976

Table 12.--Water-quality reconnaissance data for streams--Continued TOTAL TOTAL TOTAL TOTAL MERCURY NICKEL SILVER ZINC IN DIS— IN DIS— IN DIS— IN TOTAL BOTTOM SOLVED TOTAL BOTTOM SOLVED TOTAL BOTTOM SOLVED TOTAL BOTTOM MERCURY MA— NICKEL NICKEL MA— SILVER SILVER MA— ZINC ZINC MA— (HG) TERIAL (NI) (NI) TERIAL (AG) (AG) TERIAL (ZN) (ZN) TERIAL DATE (UG/L) (UG/G) (UG/L) (UG/L) (UG/G) (UG/L) (UG/L) (UG/G) (UG/L) (UG/L) (UG/G) 07186200 — CENTER CREEK NEAR FIDELITY, MO - MAP NUMBER 1 MAR 1976 07186480 — CENTER CREEK NEAR SMITHFIELD. MO._ MAP NUMBER 21 MAR 1976 <10 07186485 — TURKEY CREEK AT DUENWEG ,MO - MAP NUMBER 22 MAR 1976 07186600 — TURKEY CREEK NEAR JOPLIN, MO - MAP NUMBER 29 MAR 1976 <10 07186650 — SHORT CREEK AT MO—KANS STATE LINE - MAP NUMBER 30 MAR 1976 — —

Table 13.--Seepage-run data for Center Creek, September 1976 INSTAN­ TANEOUS DIS— DIS— SOLVED CAL­ CIUM BICAR— BONATE SPECIFIC DISCONSOLVED DUCTSULFATE ANCE TOTAL TOTAL LEAD ZINC DIS IN DIS... IN SOLVED TOTAL BOTTOM SOLVED TOTAL BOTTOM PH LEAD LEAD MA- ZINC ZINC MADATE CHARGE (CFS) (CA) (MG/L) (HCO3) (MG/L) (504) (MG/L) (MICROMHOS) (UNITS) (PB) (UG/L) (PB) (UG/L) TERIAL (UG/G) (ZN) (UG/L) (ZN) (UG/L) TERIAL (UG/G) CENTER CREEK NEAR FIDELITY MO- MAP NUMBER 1 SEP 1976 07186210 - CENTER CREEK BELOW FIDELITY. MO- MAP NUMBER 2 SEP 1976 07186730 - CENTER CREEK ABOVE GROVE CREEK- MAP NUMBER 3 SEP 1976 GROVE CREEK NEAR SCOTLAND. MO - MAP NUMBER 4 SEP 1976 07186270 -. CENTER CREEK BELOW GROVE CREEK - MAP NUMBER 5 ?00 SEP 1976 CENTER CREEK NEAR CARTERVILLE MO.- MAP NUMBER 6 SEP 1976 07186410 - CENTER CREEK BELOW LAKESIDE MO- MAP NUMBER 9 SEP . 1976 07186412 - CENTER CREEK ABOVE MINERAL BRANCH- MAP NUMBER 10 SEP 1976 07186418 - MINERAL BRANCH AT CARTERVILLE MO - MAP NUMBER 12 SEP 1976 CENTER CREEK BELOW MINERAL BRANCH - MAP NUMBER 13 SEP 1976 CENTER CREEK AT ORON0G0 MO- MAP NUMBER 15 SEP 1976 CENTER CREEK BELOW ORONOGO. MO- MAP NUMBER 18 SEP 1976 07186460 - CENTER CREEK ABOVE CARL JUNCTION, MO - MAP NUMBER 19 SEP . 1976 CENTER CREEK AT CARL JUNCTION MO - MAP NUMBER 20 SEP 1976 07186480 .. CENTER CREEK NEAR SMITHFIELD MO. - MAP NUMBER 21 SEP 1976

Table 14.--Seepage-run data for Turkey Creek, September 1976 SPE— TOTAL TOTAL DIS— CIFIC LEAD ZINC INSTAN— SOLVED DIS... CON... DIS— IN DIS— IN TANEOUS CAL— BICAR... SOLVED DUCT-. SOLVED TOTAL BOTTOM SOLVED TOTAL BOTTOM DIS... CIUM BONATE SULFATE ANCE PH LEAD LEAD MA— ZINC ZINC MA— CHARGE (CA) (HCO3) (504) (MICRO— (PB) (PB) TERIAL (ZN) (ZN) TERIAL DATE (CFS) (MG/L) (MG/L) (MG/L) MHOS) (UNITS) (UG/L) (UG/L) (UG/G) (UG/L) (UG/L) (UG/G) TURKEY CREEK AT DUENWEG, MO - MAP NUMBER 22 SEP , 1976 07186488 — TURKEY CREEK BELOW DUENWEG, MO - MAP NUMBER 23 SEP , 1976 07186492 — TURKEY CREEK ABOVE JOPLIN, MO- MAP NUMBER 24 SEP t 1976 JOPLIN CREEK AT JOPLIN, MO - MAP NUMBER 25 SEP t 1976 TURKEY CREEK AT JOPLIN, MO - MAP NUMBER 26 SEP , 1976 LONE ELM HOLLOW AT JOPLIN, MO- MAP NUMBER 27 SEP t 1976 07186600 — TURKEY CREEK NEAR JOPLIN, MO- MAP NUMBER 29 SEP , 1976 *U. S. GOVERNMENT PRINTING OFFICE: 1977--767391/26 REGION NO. 6

eS4 ae

USGS LIBRARY - RESTON 01 HMO II ,,0 H II 3 1818 001u2Y0i -.6 H

Plates & figures from the original