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James G. Brown

Publications and source records attributed to James G. Brown.

7 recordsLinked to original sources
USGS1998

Analysis and simulation of reactive transport of metal contaminants in ground water in Pinal Creek Basin, Arizona

Large-scale mining activities have generated a plume of acidic ground water more than 15 km long in the regional aquifer of the Pinal Creek Basin. A one-dimensional reactive-transport model was developed using PHREEQC to aid in the analysis of transport and chemical processes in the plume and to determine the uses and limitations of this type of modeling approach. In 1984, the acidic part of the plume had a pH as low as 3.4 and contained milligram-per-liter concentrations of iron, copper, aluminum and other metals. From 1984 to 1994, concentrations of contaminants in the alluvial aquifer in Pinal Creek Basin, Arizona, decreased as a result of mixing, recharge, remedial pumping and chemical reactions. For reactions involving gypsum and rhodochrosite, the equilibrium modeling assumption of a local geochemical equilibrium was generally valid. From 1984 to 1990, water along the simulated flow path was at equilibrium or slightly supersaturated with gypsum, and gypsum equilibria controlled dissolved concentrations of calcium and sulfate. Beginning in 1991, water in the acidic part of the plume became increasingly undersaturated with respect to gypsum, indicating that the gypsum available for dissolution in the aquifer may have been completely consumed by about 1991. Rhodochrosite precipitation was thought responsible for the measured attenuation in dissolved manganese in the neutralized zone. For reactions involving calcite, the assumption of a local geochemical equilibrium was generally not valid. Dissolution of calcite in the transition zone was not sufficient to establish equilibrium although, following neutralization, the calcite saturation index decreased to −1.2 in 1986. Calcite undersaturation decreased along the flow path in the neutralized zone, and equilibrium was attained about 7 km downgradient of the transition zone. The assumption of a local geochemical equilibrium was not valid for oxidation–reduction reactions that involved iron oxides and manganese oxides. Kinetically controlled oxidation–reduction reactions continued in the acidic part of the flow path for years following the passage of the transition zone. Although the equilibrium approach helped to provide an increased understanding of contaminant transport at Pinal Creek, future work will require a kinetic modeling approach to more accurately simulate selected reactions between the plume and aquifer materials.

Arizona↗
USGS1997

Statistical analysis of nitrate in ground water, West Salt River Valley, Arizona

Accurate estimates of the nitrate concentrations in ground water in west Salt River Valley are needed to better manage ground water affected by nitrate. Statistical analyses were done to establish the best statistical method to produce these estimates. Three sets of ground-water data for different time periods --1975-77, 1980-85, and 1986-90--were used to analyze spatial and temporal variations in concentrations of nitrate in ground water. The use of inverse-distance squared weighting, radial-basis function, kriging, and cokriging were evaluated for estimating nitrate concentrations in ground water. From an analysis of the cross-validation results, cokriging maps resulted in the best estimates, and they were accepted as being the most reliable. Cross-validation results also indicated that nitrate cokriged best with magnesium for 1975-77 and 1986-90 and with calcium for 1980-85. Kriging results consistently were almost as reliable as any of the cokriging results. Because of the difficulties inherent in the cokriging process, kriging, although not optimal, was the fastest way to obtain reasonably good results. In 1980-85, cokriged nitrate concentrations exceeded 20 milligrams per liter in a 12-square-kilometer area in Phoenix and Glendale and exceeded 10 milligrams per liter in a 280-square-kilometer area that extended to the Salt River. In 1986-90, nitrate concentrations along the entire reach of the Salt River in west Salt River Valley were less than 10 milligrams per liter and were smaller probably as a result of recharge from the Salt and Gila Rivers in 1982. Farther north in Phoenix and Glendale, the area in which nitrate concentrations exceeded 10 milligrams per liter expanded to 490 square kilometers for 1986-90. In Buckeye Valley, nitrate concentrations exceeded 10 milligrams per liter in an area of 300 square milometers for 1980-85 from the Gila River in the early 1980's but possibly could be an artifact of the different data distributions associated with each data set. In the Phoenix area, cokriged nitrate concentrations for 1975-77 exceeded 10 milligrams per liter in a 290-square-kilometer area and exceeded 20 milligrams per liter in a 1.4-square- kilometer area.

Water-Resources Investigations Report↗
USGS1996

Hydrology and geochemistry of aquifer and stream contamination related to acidic water in Pinal Creek basin near Globe, Arizona

Hydrologic and geochemical research has identified and characterized the physical and chemical processes that control the evolution and movement of metal contaminants in ground water beneath Miami Wash and lower Pinal Creek. The dissolution of calcite in the alluvial aquifer has slowed and neutralized part of the acidic plume, and the sorption of some metals such as nickel and copper to other solids in the subsurface has lowered concentrations of these metals in the ground water.

Arizona↗
USGS1989

Hydrogeology of the western part of the Salt River Valley area, Maricopa County, Arizona

The Salt River Valley is a major population and agricultural center of more than 3,000 mi 2 in central Arizona (fig. 1). The western part of the Salt River Valley area (area of this report) covers about 1,500 mi 2 . The Phoenix metropolitan area with a population of more than 1.6 million in 1985 (Valley National Bank, 1987) is located within the valley. The watersheds of the Salt, Verde, and Agua Fria Rivers provide the valley with a reliable but limited surface-water supply that must be augmented with ground water even in years of plentiful rainfall. Large-scale ground-water withdrawals began in the Salt River Valley in the early part of the 20th century; between 1915 and 1983, the total estimated ground-water pumpage was 81 million acre-ft (U.S. Geological Survey, 1984). Because of the low average annual rainfall and high potential evapotranspiration, the principal sources of ground-water recharge are urban runoff, excess irrigation, canal seepage and surface-water flows during years of higher-than-normal rainfall. Withdrawals greatly exceed recharge and, in some area, ground-water levels have declines as much as 350 ft (Laney and other, 1978; Ross, 1978). In the study area, ground-water declines of more than 300 ft have occurred in Deer Valley and from Luke Air Force Base north to Beardsley. As a result, a large depression of the water table has developed west of Luke Air Force Base (fig. 2). Ground-water use has decreased in recent years because precipitation and surface-water supplies have been greater than normal. Increased precipitation also caused large quantities of runoff to be released into the normally dry Salt and Gila River channels. From February 1978 to June 1980, streamflow losses of at least 90,000 acre-ft occurred between Jointhead Dam near the east boundary of the study area and Gillespie Dam several miles southwest of the west edge of the study area (Mann and Rhone, 1983). Consequently, ground-water declines in a large part of the basin have slowed, and ground-water levels in some sarea have risen significantly. In many areas along the Salt River and northeast of the confluence of the Salt and Agua Fria River, ground-water levels rose more than 25 ft between 1978 and 1984 (Reeter and Remick, 1986).

Arizona↗