Fate and Effects of Pollutants
Nonpoint Sources
Daniel E. Line, Gregory D. Jennings,
Richard A. McLaughlin, Deanna L. Osmond,
William A. Harman, Laura A. Lombardo,
Kevin L. Tweedy, Jean Spooner
Nonpoint source (NPS) pollution originates from diffuse land
areas that intermittently contribute pollutants to surface and
groundwater. This article is a review of 1998 literature on several
aspects of NPS pollution, including policy, economics, and management issues; effects and extent of pollutants in surface and
groundwater; pollution controls; and modeling and monitoring.
Increasingly NPS pollution reduction policy includes regulation.
Parry (1998) explained the regulatory and nonregulatory programs
developed by the U.S. Environmental Protection Agency (U.S.
EPA) to control water pollution from agricultural sources of phosphorus. Programs discussed include the Clean Water Act's definition of confined animal feeding operations (CAFOs) as point
sources, NPS program grants, the Coastal Zone Act Reauthorization Amendments of 1990; TMDLs, and the draft National Nutrient Overenrichment Assessment Strategy. More stringent controls
of confined animal feeding operations were discussed in Christen
(l998a), including U.S. EPA's Draft AFO Strategy; two congressional bills, particularly H.R. 3232 (The Farm Sustainability and
Animal Feedlot Enforcement Act); and President Clinton's Clean
Water Action Plan. Another article reported on Pennsylvania's
Nutrient Management Act, which requires high-density livestock
or poultry operations to develop and implement nutrient management plans (Christen, 1998b). Letson and Gollehon (1998) addressed the issue of manure management in times of increasing
specialization, in places where animal production is separate from
cropland. To assist policy-targeting efforts, the authors estimated
the magnitudes and locations of manure and land for its treatment.
This was done at the farm level rather than at the county level to
avoid aggregation problems.
Several articles evaluated environmental policies to control agricultural contamination. Livingston and Cory (1998) examined
the current environmental policy governing nitrate contamination
of groundwater in the South Platte alluvial aquifer in Colorado.
The typical policy choice of best management practices (BMPs)
was compared to optimal policy design, with recommendations
presented for increased effectiveness of existing policy. Oenema
and Roest (1998) discussed the pathways and controls of nitrogen
and phosphorus losses to surface waters and presented estimates
and predictions of the losses from agricultural soils to surface
waters in The Netherlands before and after implementation of
nutrient loss measures and policies. Falconer (1998) examined
some of the problems of controlling pesticide contamination in
Western Europe and the potential policy instruments for achieving
pesticide use reduction for environmental improvement.
Several articles discussed watershed-based permitting and total
maximum daily loads (TMDLs). The U.S. EPA issued its Report
of the Federal Advisory Committee on the Total Maximum Daily
Load (TMDL) Program (U.S. EPA, 1998). Hun (1998) presented
various viewpoints on the pros and cons of TMDLs, while Pelley
(1998) discussed the challenges of developing and implementing
TMDLs and presented examples of how states are implementing
the program. Another article (Galya et a1., 1998) described watershed-based management and permitting, implications for discharg1054
ers, and strategies for cost-effective TMDL solutions, including
the use of state-of-the-science study and analysis methods, regulatory involvement, pollutant trading, and participation in a watershed group.
Daniel et a1. (1998) provided a brief overview of the issues and
options related to management of agricultural phosphorus that
were discussed at a 1996 symposium titled, "Agricultural Phosphorus and Eutrophication." Topics discussed include the role of
phosphorus in eutrophication, identification of phosphorus-sensitive water bodies, phosphorus transport mechanisms, chemical
forms and fate of phosphorus, modeling of phosphorus transport,
water quality criteria, and management of soil and manure phosphorus, and phosphorus transport processes.
Land owner-operators
in central Ohio were provided the opportunity to participate in a comprehensive soil and water conservation program (Napier and Johnson, 1998). Data revealed that
conservation efforts were not very successful in motivating land
owner-operators to change production practices, which brings into
question the utility of continuing to implement soil and water
conservation practices using traditional voluntary approaches. Regarding wetland protection, a method was presented for examining
the potential economic and environmental effects of recent legislative proposals to relax the swampbuster provision of the Food
Security Act of 1985 and Section 404 of the Clean Water Act of
1977 (Claasen et a1., 1998).
The economic and environmental impacts of uniform (UAN)
and variable (V AN) application rates of nitrogen were evaluated in
a midwestern U.S. agricultural watershed (Prato and Kang, ] 998).
Tests of statistical significance were performed for differences in
nitrogen application rates, crop yields, surface and groundwater
quality, and net returns between UAN and VAN for a range of soil
and field conditions. Lee (1998) evaluated the results of 21 studies
conducted in various regions of the U.S. that examined the relationships among agrichemical treatments on crops, farm income,
and groundwater quality both at the farm level and at the aggregate
level. The author discussed tradeoffs between farm income and
groundwater quality and proposed an agenda for future research
and extension initiatives.
WATER QUALITY OF WATER RESOURCES
Surface Water. Landuse affects water quality. Researchers,
when analyzing stream chemistry and land cover in the MidAtlantic region, found Cl- to be a good surrogate for land disturbance and potential impacts from NPS pollution (Herlihy et al.,
1998). Using landuse information, drainage class, and physiographic regions, along with expert knowledge, McMahon and
Harned (1998) were able to explain water quality variations found
throughout the Albemarle-Pamlico basin in North Carolina. Water
quality trends in the Albemarle-Pamlico basin show decreasing
nutrient loading. However, the areas within the basin where nutrients and sediment loading occur are still of concern (Spruill et aI.,
1998). Harvest of loblolly pine plantations in eastern North Carolina increased annual outflow (111 to 164 mm), nitrogen export
(2.1 to 2.2 kg Nlha'yr) and phosphorus export (0.12 to 0.36 kg
Plha'yr) but during a 35-year growth cycle proved inconsequential
(Lebo and Herrmann, 1998). Landuse near Vancouver, British
Columbia, determined nitrate loading into streams from groundflow; both increased septic systems and animal production caused
stream nitrate levels to rise as high as 7 mg/L (Wernick et aI.,
1998). Nitrate levels in an agricultural drainage basin showed an
increase in stream nitrate concentration from <I mglL in 1969 to
Water Environment
Research,
Volume 71, Number 5
Fate and Effects of Pollutants
>20 mglL in 1991 as an average of 168 kg of N/ha'yr of fertilizer
has been applied during the past 26 years (Steinheimer et a1.,
f-LeqlL in unfertilized forested watersheds (Ohmi and Mitchell,
1998). Runoff was lowest for a forested system (3%) followed by
1998a). Most nitrogen and phosphorus losses from winter wheat,
spring pea, and continuous fallow plots were associated with
sediment losses, and because more sediment was lost from the
fallow fields, more nitrogen and phosphorus was lost from the
noncropped fields than the cropped fields (Douglas et a1., 1998).
Surface-applied litter production in Georgia demonstrated that
composted broiler litter, as well as fresh litter, increased dissolved
reactive phosphorus as a function of amount of phosphorus applied
(Vervoort et a1., 1998). Silica and nitrate data collected in Canajoharie Creek in New York showed seasonal patterns suggesting
that diatom growth reduces nitrate levels during summer (Wall et
aI., 1998). Sediment is still the major stream pollutant in North
Carolina, and Rudek et a1. (1998) outlined legislative and implementation failures that have not contained sediment pollution.
Aquatic insect communities are good indicators of NPS pollu-
slash/mulch (13%), plowed (17%), and pasture (31%) for subwatersheds in Matalom, Leyte, Philippines (Chandler and Walter,
1998). Researchers in China used a.distributed system of gauging
stations on streams that feed the Yangtze to determine that most of
the decreases in sedimentation are associated with the construction
of reservoirs (Lu and Higgitt, 1998). In Uganda, Lindenschmidt et
a1. (1998) collected water quality data to extrapolate nitrogen and
phosphorus loads to Lake Victoria, and they found most of the
nutrients delivered to the system are from NPSs. Pollution from
silage effluent in Northern Ireland declined by 78% from 1987 to
1995 because of pollution prevention legislation, grants, and education (Lennox et a1., 1998). Spring snowmelt was the predominant hydraulic event for exporting nitrate (55%), phosphorus
(37%), and sediment (71 %) in an agricultural watershed in Quebec
(Lapp et a1., 1998).
tion. When macroinvertebrate
communities in an agriculturally
impacted stream were compared to a nonimpacted stream, Delong
and Brusven (1998) found that lower organic matter input and
transportation and more algae reduced the number of macroinvertebrate species. In Montana, researchers found that macroinvertebrate diversity was greatest in wilderness areas and lowest in
agricultural areas (Rothrock et a1., 1998).
Different quantitative and qualitative tools are needed to determine impacts of agricultural NPS pollution. Researchers in Oklahoma, using a Matlock Pheriphytometer, determined that phosphorus, not nitrogen, is the limiting nutrient in woodland streams
(Matlock et aI., 1998). An algal assay was used to determine the
bioavailability of different phosphorus sources, and researchers
found that the wastewater treatment plant effluent was more bioavailable (72%) than rainwater (26%) or erosion effluents (30%)
(Gerdes and Kunst, 1998). Minimum detectable changes were
calculated for pollutants from an agricultural watershed (Line et
a1., 1998). To demonstrate significant changes caused by BMP
implementation, sediment required approximately a 35% reduction, whereas nitrate concentrations needed to change by only
12.6%. Using an upland agricultural watershed in Pennsylvania,
Gburek and Sharpley (1988) have begun to quantify the landscapescale hydrologic processes that control the movement of phosphorus into receiving waters. Juracek (1998) used analysis of lake
bottom sediments to estimate pollutant source loading of phosphorus: 7% from point sources and 93% from NPSs. Researchers in
France used cesium-137 to assess the magnitude of soil erosion in
a 180-ha watershed; 41 % of the watershed was stable, 45% of the
watershed had a net sediment loss, and 14% of the watershed
gained sediment (Bernard et a1., 1998).
Recreation often affects surface water quality. Sediment losses
from forest trails were largest when trafficked wet rather than dry
and from horse usage as compared to llama or people usage
(Deluca et aI., 1998). Green (1998) measured higher bulk densities
and more exposed soil in riparian campground areas than surrounding riparian areas leading to greater runoff and sedimentation
from the campground area than lower use areas.
Water quality is also of concern in many countries throughout
the world. A hydrologic study in an agrarian watershed in the
Himalayas demonstrated higher sedimentation and nutrient losses
in the farmed portion of the watershed than the agroforestry or
natural forest systems (Rai and Sharma, 1998). Researchers in
Japan measured nitrate stream concentrations in fertilized forested
watersheds at 300 f.LeqlL where 330 kg nitrogen fertilizer/ha was
applied yearly as compared to stream nitrate concentrations of 160
Understanding soil erosion processes is essential for predicting
and modeling sediment losses. Govindaraju (1998) found that the
soil loss predicted from hillslopes is very sensitive to critical shear
stress and soil erodibility. If these factors are not treated stochastica~ly, modeled soil erosion values can be under- or overpredicted.
Lane et a1. (1998) conducted a review and concluded, "there is a
severe limitation in our ability to understand erosion and sediment
yield processes as a function of spatial scale." Researchers studying freezing property of soils have found that rill erodibility during
soil freezing and thawing is highly transient and will affect the
accuracy of simulation models during winter conditions (Van
Klaveren ltnd McCool, 1998). Interrill sediment losses tend to have
smaller particle size than the in situ soil matrix (Wan and ElSwaify, 1998). The authors indicated that the wash portion of
interrill erosion, not the splash phase, produces the finer sediment
losses from interrill erosion. A laboratory setup was established
that will allow researchers to vary detachment and transport independently so that the different soil erosion processes can be better
understood (Huang, 1998). Robinson and Cook (1998) used a
hot-film anemometer to measure the hydraulic shear stress on a
channel bed to predict the boundary stress approaching the overfall
brink. Organically managed fields were only slightly less erodible
than conventionally managed fields even though measured aggregate stability and earthworm populations were greater on the
organic plots than the conventional plots (Siegrist et aI., 1998).
Erosion rates on recently tilled Conservation Reserve Program
fields were similar to conventionally tilled fields within I year
(Gilley and Doran, 1998). Boardman (1998) described how plot
data has been extrapolated and generalized for regional soil loss
estimations and explained that regionalized soil erosion data can
be extremely erroneous and misleading.
Numerous articles were written related to storm water from
urban environments. Field et al. (1998) outlined the U.S. EPA's
wet-weather flow management and pollution control research
needs and anticipated research directions for the next 5 years in the
areas of characterization and problem assessment, watershed management, toxic substance impacts and control, control technologies, and infrastructure improvement. The U.S. Geological Survey
published a report on precipitation, streamflow, and water quality
data from selected sites in the city of Charlotte and Mecklenburg
County, North Carolina, for 1995 to 1997 (Robinson et aI., 1998).
Several articles specifically discussed research on first flush
effects. Larsen et al. (1998) described results of a 2-year study in
Aalborg, Denmark, which showed significant first flush effects.
The paper also discussed the most appropriate way to characterize
Literature Review 1999
1055
Fate and Effects of Pollutants
the quality of outflow, using either the event average concentration
or the accumulated event mass. Evidence for the existence and
nature of the first flush load of pollution input to drainage systems
in Belgrade, Yugoslavia, and Lund, Sweden, was analyzed using
data on suspended solids, conductivity, pH, and temperature of
storm surface runoff (Deletic, 1998). The author concluded that (1)
the first flush, if strongly present at the end of a drainage system,
is not generated by the first flush of pollution input, and (2)
regression curves are not very reliable for prediction of the first
flush load. Bertrand-Krajewski
et al. (1998) studied 197 rainfall
events in 12 separate and combined sewer systems for the first
flush phenomenon using the dimensionless M(V) curves. The characteristics of the M(V) curves depended on the pollutant, the site,
the rainfall event, and the functioning of the sewer system, factors
which collectively prohibit the establishment of typical multiregression relationships to explain the curves' shape and variability. The authors discussed previous definitions of the first flush and
surface water resources. Water samples were collected from three
streams in the Mississippi delta during 1995 and analyzed for
selected cotton and rice herbicides and their metabolites (Coupe et
aI., 1998). The total concentration of eight herbicides and their
metabolites exceeded 5 fJ.glL throughout most of the growing
season, with a median total of 15 fJ.glL. The order of occurrence
was molinate > fluometuron > cyanazine > metolachlor > norflurazon > atrazine > prometryn > propanil. EI-Dib and AbouWaly (1998) studied the biodegradation of two triazine and two
phenylurea herbicides in Nile River water. A lag period was
evident for all compounds but decreased after the first application.
The addition of domestic wastewater decreased the lag period and
the resulting degradation period. Donald et al. (1998) assessed the
spatial and temporal variability in herbicide concentrations within
the 7250-ha Goodwater Creek watershed, Missouri. Maps of herbicide distribution established that widespread, seasonal contamination of streams in the watershed was caused by NPSs. A study
their application to the design of treatment facilities and proposed
a new definition, as one in which at least 80% of the total pollutant
mass is transported in the first 30% of the volume discharged
during rainfall events.
Deletic and Maksimovic (1998) presented results of continuous
water quality monitoring of storm runoff into a single road inlet at
two experimental catchments in Belgrade, Yugoslavia, and Lund,
Sweden. Results indicated that (1) the antecedent dry weather
period length has only a minor effect on road sediments washoff,
but it has an influence on conductivity; (2) the first flush effect of
suspended solids appeared only in a limited number of events; and
(3) suspended solids loading rate was influenced by rainfall intensity and overland flow rate. Wu et al. (1998) studied runoff
concentrations and pollutant discharge in the Piedmont region of
North Carolina, while Barrett et al. (1998) monitored runoff in
Austin, Texas.
To characterize runoff from other urban sources, deHoop et a!.
(1998) determined stormwater runoff quality from a log storage
and handling facility in Louisiana. Ryals et al. (1998) studied the
movement of fertilizers and pesticides from three southeastern
North Carolina golf courses into surface waters. Increases in
ammonium and nitrate from roof runoff in the city of Bayreuth,
Germany were measured (Forster, 1998). In addition, polycyclic
aromatic hydrocarbon concentrations were elevated near an emission source from an old heating system. Bucheli et al. (1998)
conducted a study to determine the concentration of pesticides in
roof runoff. Maximum concentrations originating primarily from
agricultural use occurred during and right after the application
periods. The study revealed that a major portion of the compounds
washed out from the atmosphere may reach the groundwater,
particularly if roof runoff is infiltrated directly into highly permeable zones of the subsurface.
Roger et al. (1998) reported the distribution of particle sizes and
the physical, chemical, and mineral characteristics of sediment
contained in runoff water in the Herault region of France. Physical
characteristics of solids transported in lateral pavement sheet flow
from a heavily traveled roadway in Cincinnati were measured
(Sansalone et al., 1998). Viklander (1998) described the physical
and chemical characteristics of sediments in northern Sweden that
had accumulated during winter and that were left at the surface
when the snow had melted. Leeming et al. (1998) examined
whether human fecal matter was the principal source of fecal
pollution in storm water drains in Victoria, Australia, as measured
by thermotolerant coliforms and enterococci.
Several studies reported on the occurrence of pesticides in
to assess the herbicide contamination of floodwaters and farmland
resulting from the great flood of 1993 was conducted (Chong et a!.,
1998). Concentrations of alachlor, atrazine, and cyanazine in water
and suspended sediment samples, collected from August 1993
through December 1993, were below the health advisory concentration of 3 fLglL for all samples. Soil samples collected after
flooding at two of three sampling locations had a 0.4 to 0.8 fJ.glkg
increase in atrazine as compared to nonflooded sites.
Battaglin and Goolsby (1998) developed multiple linear and
logistic regression equations to model mean herbicide concentrations in reservoir outflow as a function of landuse, agricultural
chemical use, climatic conditions, topographic character, and soil
type of the drainage basin. There was a strong association between
mean herbicide concentrations in reservoir outflow and herbicide
use rates within associated drainage basins. An economic perspective on residential outdoor pesticide use was presented (Templeton
et a!., )998). During the past 20 years, pesticides for non structural
pests have been applied on residential landscapes of approximately
50% of all U.S. households. Typically, homeowners are less likely
than farmers to use pesticides, read labels, and take precautions.
These behavioral differences between household users and farmers
reflect differences in the objectives and degree of market orientation of pest control, the scale of operations, and regulation.
Several researchers conducted studies of specific pesticides and
their effects on water quality. Lerch et al. (1998) presented research on the contribution of hydroxylated atrazine degradation
products (HADPs) to the total atrazine load to streams in nine
midwestern states. Atrazine metabolites accounted for nearly 60%
of the atrazine load in northern Missouri streams at preplant. An
experiment to assess the effects of postapplication irrigation depth
and formulation (liquid or granular) on concentration and transport
of diazinon in runoff from tall fescue was performed (Evans et aI.,
1998). Postapplication irrigation depth had no effect on diazinon
concentrations but increased diazinon mass transported caused by
increased runoff volume. Mean runoff diazinon concentration for
the liquid formulation was roughly double that of the granular
formulation of diazinon.
Groundwater.
Wong et al. (1998) performed a Iysimeter study
to evaluate the leaching losses of nitrate, ammonium, and phosphate fertilizer from golf course turfgrass. The current application
rate of fertilizer on greens can create adverse environmental conditions on the surface water and groundwater caused by leaching
losses of phosphate and nitrate. In another Iysimeter study conducted on com-alfalfa rotation cropland, researchers concluded
that including alfalfa in a rotation with fertilized com would result
1056
Water Environment Research,
Volume 71, Number 5
Fate and Effects of Pollutants
in a considerable reduction in the amount of nitrate leaving a farm
as leachate (Toth and Fox, 1998). Fenelon and Moore (1998)
reported on the occurrence, distribution, concentrations, and pathways of agrichemicals in the Sugar Creek watershed, Indiana.
They concluded that tile drains directly affected the water quality
in Sugar Creek by transporting soil pore water and shallow
groundwater containing high concentrations of nitrate and pesticides to the creek. In a study of bromide leaching under various
cropping scenarios, the impact of crop type on the rapid movement
of bromide was minimal, and there was greater potential for
shallow groundwater pollution by nonadsorbed agrichemicals exists on medium-textured silt loam soils than previously believed
(Iragavarapu et aI., 1998). Thomsen and Christensen (1998) evaluated the effect of cropping system and crop residue management
on crop yield, nitrogen uptake, and nitrate leaching in a 2-year
lysimeter study. Amounts of nitrogen exported in the crop rotation
by nitrate leaching and plant uptake typically balanced the
amounts of nitrogen applied in mineral fertilizer.
In a study of phosphate transport in undisturbed soil columns,
the positive correlation observed between concentration of dissolved orthophosphate and field effluent discharge rate was restricted to rainfall intensities that initiated preferential flow (Jensen
et aI., 1998). Phosphorus transport increased the more dilute the
percolating solution remained. Sims et al. (1998) presented a
review of research on phosphorus leaching and export in subsurface runoff and presented overviews of ongoing research in the
Atlantic Coastal Plain, the midwestern U.S., and eastern Canada. A
lysimeter study of phosphorus and bromide transport in clay soil
revealed that phosphorus losses were dominated by flux and that
rainstorms had to reach a certain intensity to initiate total phosphorus and particulate phosphorus losses (Ulen et aI., 1998).
Stamm et a1. (1998) investigated the phosphorus export from two
drainage systems under intensively used grassland in a catchment
of the Swiss Plateau. The discharge-concentration
relationship
indicated that phosphorus was transported through preferential
flow paths extending from close to the surface to the drains. More
than one-half of the yearly soluble reactive phosphorus load was
leached from an artificially drained, phosphorus-enriched soil, and
in the investigated watershed, leaching and not surface runoff was
the most important mechanism for phosphorus transfer from soils
to surface waters (Gachter et aI., 1998). To develop a model to
estimate phosphorus export from cropland, Xue et al. (1998)
studied dissolved phosphorus output from four tile drains in east
central Illinois. For the study watershed, a first-order, one parameter equation could estimate watershed wide dissolved phosphorus
export.
Several studies were published that reported on groundwater
quality of specific geographical areas. Massone et al. (1998) presented an analysis of the relationship between landuse and groundwater pollution in the suburban area of Mar del Plata, Argentina.
Fifty wells in an area of 175 km2 were sampled, and the data
revealed three elements that were endangering the quality of
groundwater: horticultural activity, urban solid waste disposal
sites, and wastewater disposal on land. A groundwater monitoring
study initiated in the Herrings Marsh Run watershed, North Carolina, concluded that nitrate-nitrogen contamination of groundwater
was not a widespread problem within the watershed (Stone et aI.,
1998). Sixteen of 21 monitoring wells sampled within the watershed had mean concentrations of nitrate-nitrogen < 10 mglL.
Zebarth et a1. (1998) evaluated spatial and temporal variation of
nitrate contamination in a study area within the Canadian portion
of the Abbotsford-Sumas
aquifer that covers an area of 100 km2•
Literature
Review 1999
Agricultural production was cited as a primary contributor to
elevated nitrate concentrations, which were observed over a wide
portion of the aquifer. Steinheimer et a1. (1998b) studied a 40-ha
field in the loess hills of southwestern Iowa to determine the
impact of com production in ridge-tilled soils on nitrate loading in
groundwater. Leaching resulted in the drinking water maximum
contaminant level (MCL) being exceeded for several wells
screened within the saturated loess. Because of relatively rapid
conductance of both water and applied agrichemicals, the loess
hills represent a vulnerable agricultural landscape on which nitrogen fertilization affects groundwater quality. A two-part study was
conducted to evaluate the quality and safety of groundwater supplies in Ontario, Canada, farmstead domestic wells. In the first part
of the study, Goss et al. (1998) sampled drinking water from
domestic wells and found that approximately 40% of tested wells
contained one or more of the target contaminants above the maximum acceptable concentration. For the second part of the study,
Rudolph et a1. (1998) installed multilevel monitoring wells at 144
farms that were part of the first study. Results from the sampling
were consistent with those obtained from the first part of the study,
indicating the utility of water well survey data for assessing
groundwater quality within the rural environment. The quality of
groundwater in the Sierra Pelona watershed, California, was evaluated, and there were three patterns of nitrate contamination: (I)
isolated wells affected by numerous, localized nitrate sources; (2)
a tight cluster of wells, unusually low in other ions but consistently
high in nitrate; and (3) moderate to typically consistent nitrate
concentrations found over a large, diffuse region of the Sierra
Pelona alluvial aquifer (Williams et al., 1998). Robins (1998)
conducted a study to evaluate the quality of shallow groundwater
in Northern Ireland, concluding that the relatively high rainfall in
the area dilutes surplus nutrients, which, combined with the yearround moist soils with an active bacterial population, ensures that
nitrate-nitrogen concentrations are generally low.
Animal production facilities are often cited as sources of nutrients and bacteria that can contaminate groundwater. Stone et a1.
(1998b) studied the change in groundwater and surface water
concentrations of nitrogen and phosphorus as a result of a swine
farm increasing its size from 3300 to 14 000 animals. Stream
nitrate concentrations remained constant during warmer months
but increased during colder months, along with increased nitrate
concentrations in three of seven monitoring wells. A riparian zone
on site reduced the effect of spray field groundwater nitrate concentrations and ammonia loadings in an adjacent stream. Scott et
a1. (1998a) presented monitoring data on phosphorus and fecal
coliforms measured under conditions of preferential flow through
macropores and steep slopes that increase drainage in shallow,
permeable soils on a hardpan. They concluded that under some
conditions, the contaminant discharge from subsurface drains may
have significant water quality effects on receiving waters. A lysimeter study was conducted to evaluate the potential for nitrate
leaching losses under management intensive grazing (Stout et aI.,
1998). The researchers concluded that if use of management intensive grazing continues to increase, the amount of nitrogen
leached to the groundwater from beneath urine patches could
become substantial and have on- and off-farm impacts. Based on
information from ten swine farms and two dairy farms, the report
concluded that the lagoon construction standards, or the process of
implementing the standards, are apparently insufficient for the
prevention of groundwater contamination. For an Ontario, Canada,
field, significant amounts of bacteria can reach surface waters by
infiltrating through the soil and traveling through subsurface tile
1057
Fate and Effects of Pollutants
drains to the receiving waters, even under accepted liquid manure
loading rates (Joy et aI., 1998). McMurry et al. (1998) conducted
an experiment to evaluate the preferential flow of fecal coliforms
through undisturbed soil blocks receiving poultry waste. They
concluded that rainfall on a well-structured soil will cause the
preferential movement of fecal bacteria, even with unsaturated
conditions, and could contribute to fecal coliform concentrations in
shallow groundwater. Stoddard et al. (1998) performed a field
experiment to measure fecal coliforms and fecal streptococci in
leachate from dairy manure-amended no-tillage and conservation
tillage soils. The potential for groundwater contamination depended on soil structure and water flow more than on fecal bacteria
survival at the soil surface. Repacked soil columns were used to
study the movement of bacteria in unsaturated soils (Abu-Ash our
et aI., 1998). A significant increase in the number of bacteria cells
passed through a soil column when macropores were present and
the soil was wet.
A survey of surface and groundwater in Bangladesh for organochlorine insecticide residues indicated relatively little contamination above health guidelines, although increased usage may change
these results (Matin et aI., 1998). Novak et al. (l998a) conducted
a shallow groundwater survey during three years in a North Carolina Coastal Plain watershed, finding 91 % of the wells with no
detection of 11 commonly used pesticides. A more widely distributed survey of groundwater in North Carolina found 23 pesticides
or degradation products and a total of 26 of 97 wells with detections (Wade et al., ]998). No relationship was found between
several leaching indices and the survey results. Kolpin et al. (1998)
published a summary of 41 studies conducted by the U.S. Geological Survey which examined the occurrence of pesticides in
groundwater from 1993 to 1995. Of the I 034 sites sampled,
54.4% had detectable residues, including atrazine (38.2%), deethylatrazine (34.2%), simazine (18.0%), metolachlor (14.6%), and
prometon (13.9%). Drinking water standards were exceeded in
only one we]1. In a related article, Ko]pin et al. (1998) examined
and its major degradation product, 3,4-dichloroaniline, were monitored in rice field, and both were found to have very short
half-lives of less than 2 days. Shapir et al. (1998) inoculated
aquifer sediments with a strain of Pseudomonas sp. and determined that atrazine could be largely mineralized under nitratereducing conditions. The addition of a carbon source increased
degradation rates, especially at high atrazine concentrations (10
ppm). A mixed culture of plant pathogenic fungi was determined
to degrade the insecticide chlorpyrifos more quickly than any
single culture of the eight fungi (AI-MiHanna et aI., 1998). The
authors suggested that a soil with an active microbial population
would be more effective in degrading pesticides.
This theme was continued in a paper in which biodegradation
rates of 2,4-dichlorophenoxyacetic
acid (2,4-D) were determined
at depths of 0 to 40 em and in the subsoil at 40 to 50 em (Shaw and
Bums, 1998a). After 83 days, 50 to 60% of the 2,4-0 was completely mineralized in the top horizon, but the range was 5 to 56%
in the subsoil. Inocu]ating the subsoil with topsoil brought the
mineralization up to >50%, while nutrient and carbon source
amendments did not. Mineralization correlated well with degradation rates, and uneven distribution in the subsoil was the explanation for the variable mineralization rates.
Shaw and Bums (l998b) also examined the fate of 2,4-0 in soil
columns under different irrigation flow rates and temperatures., and
after mu]tiple applications. Reducing the flow from 1.8-cmJd to
0.9-cmJd increased degradation from 45 to 73%. Increasing the
temperature from 4 to 20°C also significantly increased degradation rates and reduced leaching losses. Enhanced biodegradation
was evident after multiple applications. Langer et al. (1998) also
found degradation rates of 2,4-D were strongly influenced by
residence time and pore water velocity. The authors indicated that
changing the velocity could affect many aspects of the process of
transport and degradation, resulting in no clear first-order rate
constants for all conditions. Similarly, Frick et a!. (1998) found
that a soil fumigant, methyl isothiocyanate, was more readily
herbicide metabolites in Iowa groundwater and found them to be
much more prevalent than the parent compounds. They recommended all herbicide investigations include these metabolites.
A study of two soil fumigants, 1,2-dichloropropane (l,2-DCP)
and 1,3-dich]oropropene in groundwater found the former in 32 of
40 locations but the latter in only one (Grove et aI., 1998a).
Although these compounds had been banned for several years, the
authors concluded there is a reservoir of 1,2-DCP in the soil, which
is continuing to contaminate the aquifer. Springer and Bair (1998)
injected a small amount of bromide, atrazine, and alachlor into
shallow groundwater to determine natural-gradient transport. They
found that atrazine and a]achlor were highly retarded, with retardation factors of 6.1 and 7.1, respectively. These values were two
to three times larger than laboratory batch measurements.
The relative leaching potential of trifluralin, meto]achlor, and
metribuzin was determined in a silty clay loam soil using batch
adsorption and soil column experiments (Kim and Feag]ey, 1998).
As expected, the leaching potential order was trifluralin > metolachlor > metribuzin.
Cogger et al. (1998a and 1998b) published two companion
papers on the fate of simazine and carbofuran in alluvia] soils in
western Washington. In the first, simazine had a half-life of 128 to
175 days and was found in monitoring wells at relatively low
concentrations. Enhanced degradation reduced the leaching risk of
carbofuran and residues in monitoring wells declined each year. In
both cases, nonequilibrium adsorption appeared to increase persistence compared to predictions using the PRZM model. Propanil
leached with more frequent water application or decreasing lag
times between injection and water application. Significant volatilization losses occurred when water application was delayed, with
up to 30% lost by this route. Overall, they concluded that rapid
degradation and volatilization would preclude significant leaching
of this compound under most conditions.
Streptomyces sp. exhibited the ability to degrade atrazine in
sterile soil, particularly when it is amended with substrate (chitin
and cornstalks) and phosphate (Fadullon et aI., 1998). A soil
amendment reported to have fertilizer and insecticidal properties,
neem cake, was tested in the laboratory for effects on the persistence of two insecticides, diazinon and endosulfan (Akhtar et aI.,
1998). The neem cake appeared to reduce degradation rates of both
compounds when applied at rates of 1 to 3 tons ha -I. The effect of
tillage practices on alachlor dissipation and leaching was studied in
both soil columns and field samples in Iowa (Weed et aI., 1998).
The half-life was 3 days or less, with 90% dissipated within 17 to
30 days. Leaching losses below 30 em were somewhat greater in
no-till (1.4%) compared to chise]-plow tillage (0.4%), but dissipation rates were somewhat higher.
Sorption processes were studied under a number of conditions
and using various approaches. Johnson and Sims (1998) compared
two methods of measuring adsorption of atrazine and dicamba: soil
thin layer chromatography (soil-TLC) and batch equilibrium. The
resulting adsorption coefficients (Kd) were significantly different,
and they suggested the soil- TLC better represented the processes
that occur in the field. Hu and Brusseau (1998) examined the
1058
Water Environment
Research,
Volume 71, Number 5
Fate and Effects of Pollutants
interactions of sorption processes with biodegradation to describe
the transport of 2,4-dichlorophenoxyacetic
acid in soil columns.
Both nonlinear and rate-limited sorption was evident when solute
concentrations were increased. Using non sterile soil columns, they
demonstrated that adding the biodegradation component enhanced
soil interactions to retard leaching. The interactions among specific
soil components
and atrazine,
deethylatrazine,
and hydroxyatrazine were described (Moreau-Kervevan
and Mouvet,
1998). Hydroxyatrazine was more highly adsorbed than the other
two chemicals on all three components tested: iron oxides, clays,
and humic acid. Humic acid was more adsorbent for all three
compared to mineral components. In a similar study, the adsorption characteristics of three imidazolinone herbicides were determined on humic acids and soils (Gennari et al., 1998). These
compounds can carry positive, negative, or no charge depending
on pH. Little adsorption occurred on soils of neutral pH. Imazapyr
and imazaquin adsorbed similarly and less than imazethapyr, and
organic malter, amorphous iron oxides, and iron-organic complexes all seemed to provide some adsorption.
Atrazine and metolachlor were more easily desorbed when
applied to soil at the same time or in a commercial mixture,
suggesting greater mobility under these conditions (Farenhorst and
Bowman, 1998). In a similar study, Martins and Mermoud (1998)
found that adsorbtion and biodegradation decreased when four
nitroaromatic herbicides were introduced as a mixture compared to
each one alone. Increased ionic strength of the solute increased
sorption, suggesting soil solution chemistry can affect the herbicide-soil interactions. This concept was further explored in an
examination of the effects of naturally occurring aromatic acids on
two synthetic compounds used as models of common pollutants
(Xing and Pignatello, 1998). Sorption of the two synthetic compounds was reduced up to 42% by concentrations of the aromatic
acids similar to those under natural conditions. The sorption sites
were primarily on the soil organic matter fraction.
One aspect of adsorption in soil has been largely ignored but
may be important, according to Liu et al. (1998). They found that
cyanazine can be bound by microbial biomass in culture, resulting
in potentially erroneous conclusions that degradation occurred.
Metolachlor did not exhibit this behavior.
BMPS FOR NPS CONTROL
Monitoring studies of agricultural BMPs included projects to
evaluate pollution prevention, trapping, and remediation techniques at the field and watershed scales. Gascho et al. (1998)
reported that liquid fertilizers were not as susceptible to surface
runoff as solid fertilizers in corn plot studies in Georgia. Bengston
et al. (1998) measured nutrient and pesticide runoff from sugarcane fields in Louisiana under varying application rates and found
large differences in runoff water quality depending on inputs. Rye
winter cover crops cannot be counted on to reduce nitrate leaching
in Mid-Atlantic states based on research in corn production systems in Delaware (Ritter et aI., 1998). Ertl et al. (1998) reported
that low phytic acid corn grain fed to chickens resulted in reduced
phosphorus in the poultry waste to be released into the environment. Sprinkler irrigation on cropland caused greater watershed
runoff of sediment, nutrients, and pesticides than furrow irrigation
methods in Washington (Ebbert and Kim, 1998).
Conservation tillage practices increased runoff and reduced soil
loss from com and soybean fields in Missouri (Ghidey and Alberts,
1998). Bjorneberg et al. (1998) reported reduced subsurface drainage of nitrogen for no-tillage practices combined with split nitroLiterature Review 1999
gen fertilizer applications on corn and soybeans in Iowa. Research
on chemical leaching in Ontario corn fields indicated no effects of
tillage on groundwater nitrate (Patni et al., 1998) and increased
atrazine leaching under no-tillage compared with conventional
tillage (Masse et al., 1998). Schreiber and Cullum (1998) reported
higher nutrient concentrations in surface runoff from a no-till
soybean watershed in Mississippi than from a similar conventional-till watershed. Uri (1998) reported that the profile of a farm
adopting conservation tillage in 1987 had above average slope and
experienced above average rainfall. The farm was a cash grain
enterprise, and it had an above average expenditure on pesticides
and below average expenditures on fuel and custom pesticide
applications.
Franti et al. (1998) and Mickelson et al. (1998) measured
herbicide runoff from tile-outlet terraces in Iowa, Nebraska, and
Missouri and found that soil incorporation and no-tillage were
more effective in reducing herbicide losses than were setbacks.
Watertable management was effective in reducing pesticide leaching in Quebec (Jebellie and Prasher, 1998) and nitrate leaching in
Ontario (Tan et al., 1998).
Brown et al. (1998) reported soil loss reductions up to 98%
when Idaho furrow irrigation systems were treated with straw and
cottage cheese whey. Lentz et al. (1998) and Sojka et al. (1998a
and 1998b), evaluated the effectiveness of polyacrylamide (PAM)
for erosion control in furrow irrigation systems in Idaho and
reported large increases in infiltration and decreases in sediment,
phosphorus, and organic material transport from treated fields.
Aase et al. (1998) found that PAM applied to soil through sprinkler
irrigation systems reduced runoff and erosion. Perrin et al. (1998)
reported nitrogen leaching reductions from sandy soils treated with
the zeolite mineral, c1inoptilolite. The nitrification inhibitor dicyandiamide (DCD) was effective in reducing nitrate leaching in
Iysimeters treated with high nitrogen dairy farm effluent in New
Zealand (Williamson et al., 1998).
Ginting et al. (1998a and 1998b) studied corn yield, runoff, and
sediment and nutrient losses affected by beef cattle manure and
tillage management systems in Minnesota and found that ridge
tillage and manure applications were beneficial to water quality.
Gilley and Edhball (1998) reported environmental benefits of beef
cattle manure and compost applied to grain fields in Nebraska
under no-till and tillage conditions. A watershed monitoring study
in Quebec indicated significant reductions in phosphorus and bacteria following implementation
of animal waste management
BMPs (Gallichand et al., 1998).
Grass buffer strips were effective in reducing wheat fertilizer
runoff in England (White et al., 1998), dairy loafing lot runoff in
Virginia (You nos et al., 1998), beef cattle pasture runoff in Kentucky (Lim et al., 1998), swine lagoon wastewater runoff in Alabama (Hawkins et aI., 1998), and poultry waste runoff in Kentucky
(Coyne et al., 1998). Pollutant reductions measured in these studies
were as high as 98%, with variations related to pollutant loading,
buffer length, and site conditions. Hubbard et al. (1998) found that
grass buffers in combination with established riparian forested
buffers were very effective in assimilating swine waste lagoon
wastewater runoff in Georgia. Water quality benefits of riparian
forested buffers were demonstrated for nutrient reductions in Virginia (Snyder et al., 1998), nutrient and pesticide reductions in
Kentucky (Barfield et al., 1998), and phosphorus retention in
Rhode Island (Lyons et aI., 1998). Gold et al. (1998) and Jacinthe
et al. (1998) found that concentrated organic matter regions in
forested riparian buffers have a great impact on nitrate removal
and microbial nitrogen transformations in Rhode Island. Runoff
1059
Fate and Effects of Pollutants
dispersal in forested filter zones in North Carolina increased denitrification potential but did not result in higher denitrification
caused by limited carbon availability (Verehot et aI., 1998).
Whichert and Rapport (1998) used fish community structure monitoring to show the value of reestablishing riparian buffers in
agricultural watersheds in Ontario.
The performance of constructed wetlands in treating poultry
wastewater was shown to improve with increasing temperature in
Alabama (Hill and Payton, 1998). Ingersoll and Baker (1998)
found that the nitrate-removal performance of constructed wetlands increased with increasing carbon addition and decreasing
hydraulic loading rates in Arizona. Hill and Sobsey (1998) measured large bacterial and viral indicator reductions in North Carolina swine wastewater treatment systems, including anaerobic lagoons and constructed wetlands. Lusby et aI. (1998) reported that
plants played a central role in the ammonium processing capacity
of lake edge wetlands in New Zealand. Agricultural watershed
runoff treatment by pond systems in China depended on pond
storage capacity, rainfall, and irrigation (Yan et aI., 1998).
Forest harvesting BMPs greatly improved water quality in Kentucky watersheds (Arthur et aI., 1998). Amatya et aI. (1998)
reported nutrient and sediment export reductions in North Carolina
pine plantation watersheds using controlled drainage. Grace et al.
(1998) found large reductions in sediment yields resulting from the
use of erosion mats and grasses on constructed forest roads in
Alabama.
Stream channel migration and resulting sedimentation was
much higher for un forested streambanks than for forested banks in
Missouri (Burckhardt and Todd, 1998). Rice and Kadavy (1998)
presented design criteria for a structural low-drop grade-control
North Carolina can be effective for removal of nutrients, particularly during summer months and with high pollutant loadings.
Duckweed mixtures were effective in removing nitrogen and phosphorus in an urban storm water constructed wetland in Minnesota
(Perniel et aI., 1998).
A 90% removal efficiency was achieved for TSS, COD, BOD,
hydrocarbons, and E. coli from combined sewer overflow outlet
serving a treatment process using a storage basin, chemical flocculation, sludge removal, sand filtration, and UV disinfection
(Laine et aI., 1998). A Lamellae settler prototype removed 70%
suspended solids and 60% COD in urban stormwater runoff (Bridoux et aI., 1998). Pisano (1998) described a flow gauge tested in
Germany to collect storm overflows from combined sewer systems.
A diverse set of innovative and alternative onsite wastewater
treatment systems were discussed in a series of papers (Sievers,
1998), as well as failure analysis, site and soil evaluations, education and training, regulations, and water quality issues. Katers
and Zanoni (1998) proposed a modified conventional septic tank
system that allows for a biological growth column for nitrification,
followed by an anoxic zone for denitrification.
structure intended to stabilize degrading stream channels.
Methods to treat urban stonnwater were investigated. Thorolfsson (1998) outlined an increased acceptance in Norway to mimicking natural processes (e.g., infiltration and ponds) for urban
storm water control and restoring the natural function of the watershed streams. D' Arcy et aI. (1998) suggested that control of
nonpoint pollutant sources in the U.K. can be accomplished by a
combination of government bans and tax incentives, which have
resulted in a decrease in chlorinated hydrocarbons and lead, as well
as voluntary efforts based on educational guidance on cost-effective BMP effectiveness.
Barrett et al. (1998a) demonstrated that highway medians can
act as effective vegetative filter strips and remove greater than 85%
of suspended solids and 68 to 93% of turbidity from highway'
runoff. In contrast, total suspended sediment removal from highway construction sites by geotextile silt fences was solely related
to the detention time of the impounded runoff behind the fence
with no sediment removal resulting from filtration (Barrett et aI.,
1998b). Concurrently, the silt fences did not reduce turbidity.
Stormwater detention ponds were effective at reducing solids
and particle-associated pollutants (e.g., TSS and lead) from highway runoff but did not reduce dissolved pollutants (Pettersson,
1998). Pollutant removal benefits of decentralized stormwater
treatment with conversion of retention basins to soil filtration
systems (Sieker and Klein, 1998) or vegetative swale/trench-soiV
gravel infiltration systems (Sieker, 1998), as compared to centralized storm water treatment systems, were discussed. Przepiora et aI.
(1998) demonstrated significant reductions in discharge water turbidity (to <50 NTU) from sediment basins equipped with a
floating skimmer device by using moulding plaster (CaS04'O.5
H20) as a chemical flocculant.
Borden et aI. (1998) demonstrated that wet detention ponds in
the measured daily erosion series. Both measured and predicted
frequency curves fell within the 95% confidence range of a Log
Pearson Type III distribution, even using synthetic weather series
generated with the CLIGEN model. A model was developed to
predict interrill sediment delivery (Zhang et aI., 1998 and I 998b ).
The model showed that among the parameters of discharge, rainfall intensity, and slope steepness, discharge had the greatest
correlation with sediment delivery; neither discharge nor rainfall
alone could adequately simulate interrill sediment delivery. Lisle
et al. (1998) used a stochastic sediment transport model to establish a theoretical link between the Hairsine-Rose erosion model
and the bedload model of H. Einstein. A method was provided for
improving SWAT (soil and water assessment tool) stream runoff
prediction in ungauged watersheds (Manguerra and Engel, 1998).
Grove et al. (l998b) compared composite versus distributed approaches to estimating a NRCS curve number (CN). Simulations
indicated that significant errors occurred when composited rather
than distributed CNs were used. Combining experimental data and
simulated water quality impacts of farming systems using SWAT,
Qiu and Prato (1998) estimated the water quality benefits of
riparian buffers. Results strongly supported the development and
maintenance of riparian buffers.
Chen et aI. (1998a and 1998b) developed a series of computational procedures identifying the geometric relationships among
the sun position, stream location and orientation, and riparian
shading characteristics to develop SHADE. The SHADE-generated data solar radiation data are used by HSPF to simulate hourly
stream temperatures that can be used for relating riparian forest
management to stream temperature. The critical data requirements
for predicting erosion and sedimentation in western mountain
drainage basins were discussed (Dunne, 1998). Despite short baseline monitoring periods and less than four years of highly variable
1060
NPS MODELING AND MONITORING
Modeling. Mahamah (1998) discussed the most frequently used
assumptions in quantitative water quality models, including
steady-state, complete-mixing, and first-order kinetics. Baffaut et
al. (1998) analyzed frequency distributions of measured daily soil
loss values to determine if the Water Erosion Prediction Project
(WEPP) model accurately reproduced statistical distributions of
Water Environment
Research,
Volume 71, Number 5
Fate and Effects of Pollutants
data, analytical methods consistently verified phosphorus reductions from BMPs for a wide range of cropping systems in south
Florida (Rice and Izuno, 1998). Srivastava et a1. (1998) conducted
a study to validate an event-based model that simulates soluble
nutrient transport in vegetative filter strips using data from a field
plot. Accurate prediction of infiltration and runoff was critical for
accurate prediction of mass transport.
Sedimentation
algorithms in the WEPP-SIE (Surface Impoundment Element) were discussed and verified (Lindley et
aI., 1998a). WEPPSIE performed adequately with 11 field data
sets with an average trapping efficiency prediction error of
5.5%. The WEPPSIE model also performed accurate hydraulic
routings for impoundments covering a wide range of geometries
and outflow structures (Lindley et a1., 1998b). Meals and Budd
(1998) used landuse data, an export coefficient model, and a
regional hydrologic database to estimate NPS phosphorus loads
to Lake Champlain. Agriculture contributes 66% of the annual
NPS phosphorus load, and urban and forest land contribute 18
and 16%, respectively. Mass balance and dynamic simulation
modeling could describe the phosphorus cycling, storage, and
export for watershed ecosystems over a range of spatial and
spatial analyses of pollutant runoff loads in agricultural watersheds (Ha et aI., 1998).
Historical landuse and dairy herd data were synthesized with
hydrologic model 'simulations and soluble phosphorus concentration data to investigate trends in the watershed phosphorus loading
to streams (Scott et aI., 1998). Soluble phosphorus loading was
heavily influenced by manure application, particularly on com
land. Sun et al. (1998a) used the FLATWOODS model to evaluate
the hydrologic impacts of forest harvesting on Florida flatwoods.
Simulations suggested that pine flatwoods are hydrologic storage
areas where groundwater table dictates the surface runoff. In
another study, the FLATWOODS was used to model the forest
hydrology of wetland-upland
ecosystems in Florida (Sun et aI.,
1998b). Davis et a1. (1998) presented the catchment management
support system (CMSS) to assist in preparing nutrient management
plans in Australia. Atkinson et a1. (1998) developed procedures to
allow linkages between finite-difference hydrodynamic and water
quality models having different temporal and spatial scales by
defining values for the mean flow and dispersion coefficients.
Results from a case study were used to confirm the validity of the
procedures. A methodology was developed for determining the
time scales (Cassell et aI., 199&). Tufford et a1. (199&) developed multiple regression models relating landuse to in-stream
concentrations of total nitrogen and phosphorus in eight watersheds on the coastal plain of South Carolina. All models except
two were significant at P < 0.05. Kinnell and Risse (1998)
demonstrated that the USLE-M (universal soil loss equationModified) offers an improvement over the USLE because it is
better suited to predicting erosion caused by small to medium
storm events.
The RUNOFF simulation model was used to estimate sediment
yield from an agricultural watershed in China (Van Liew, 1998).
RUNOFF estimated sediment yields to within ±30% of the measured values for 20 out of 24 events. Yu and Schwartz (1998)
developed a physically based, distributed-parameter
model, the
basin-scale hydrologic model (BSHM), for predicting the hydrologic response from large drainage basins. Heng and Nikolaidis
(1998) developed a physically based, energy driven, multiple
landuse, distributed model called NTT -Watershed (nutrient transport and transformation). The NTT-Watershed model was capable
of capturing the hydrologic portions of the nitrogen dynamics and
could be used to develop BMP strategies to reduce nitrogen export
from a watershed. A mass balance approach was implemented to
predict nutrient fate of manure from beef cattle feedlots in a Visual
Basic framework (Eigenberg et al., 1998).
Fraser et a1. (1998) presented GIS-based transport model
(SEDMOD) that provides an index of pathogen loading potential from NPSs to streams. Procedures for designing grid-cell
layouts using geostatistical methods were applied to the agricultural nonpoint source pollution (AGNPS) model (Brannan
and Hamlett, 1998). The authors concluded that further development and application of the geostatistical methods will lead
to greater improvements in the simulation accuracy of spatially
distributed models including AGNPS. Whittemore (1998) provided an overview of U.S. EPA's better assessment science
integrating point and nonpoint sources (BASINS) model. BASINS was developed by the U.S. EPA to help states develop
total maximum daily loads (TMDLs) in a GIS environment.
Loague et al. (1998) discussed the challenge of predicting NPS
pollution and how GIS can assess soil and groundwater contamination by pollutants. A GIS model was developed for
1998). In general, the decision risk increased as the input variation
increases. Williams (1998a) presented a conceptual model to estimate the concentrations of pesticides appearing in surface waters
following their application as part of agricultural production. The
model specifically addresses soils that are prone to bypass flow and
require artificial subsurface drainage. The author tested this model
against data collected from a catchment study (Williams, 1998b).
The model provided estimates of observed data within an order of
magnitude for both the total pesticide loss and peak concentrations.
Modeling pollutant movement go groundwater continues to be
the subject of research. Navulur and Engel (1998) showed that the
DRASTIC and SEEPAGE models are valuable as screening tools
by comparing modeling results with well water quality data from
across the state of Indiana. A stochastic model for the evaluation
of the vulnerability of soils to nitrate leaching considering the soil,
water, and crop management conditions of the area was used to
map the nitrate leaching hazard of areas in Hungary (Nemeth et a!.,
1998). Trabada-Crende and Vinten (1998) applied the nitrogen
cycle models ANIMO and N-CYCLE to a nitrate vulnerable zone
area in Fife, Scotland, and determined that achieving a nitrate
concentration which complies with the EC legislation would require replacing all current intensive rotations in the catchment with
only cereals and grass.
A neural network model was used successfully to simulate
nitrate leaching in agricultural drainage under various management
systems (Kaluli et al., 1998). Pang et al. (1998) validated the
CERES-Maize model using 2 years of experimental nitrate leaching data and then used the model to show that an irrigation trigger
deficit as low as 30% had little effect on com yield but significantly reduced nitrate leaching over the 31 years of the simulation.
After calibrating and validating the nitrogen and carbon cycling in
soil and water and plant (NCSW AP) model using data from a silt
loam soil of central Pennsylvania, Jabro et a!. (1998) concluded
that the model accurately simulated water flow and total annual
nitrate leaching below the I-m depth under an orchardgrass pasture.
The nitrate leaching and economic analysis package (NLEAP)
was modified to simulate the effects of crop rotations and other
management practices on nitrate leaching below the root zone
(Delgado et aI., 1998a). Delgado et al. (l998b) calibrated and
Literature Review 1999
decision-making risk from AGNPS simulations (Parson et aI.,
1061
Fate and Effects of Pollutants
validated the NLEAP model using an extensive data set from south
central Colorado and used the model to demonstrate that the net
process of nitrate leaching can be reversed when BMPs are implemented. The NLEAP model was used to show that, with a
careful and conservative nitrogen management strategy, a consistently low annual field nitrogen balance, and thus a low nitrate
leaching potential can be maintained on a central Pennsylvania
dairy farm (Saporito and Lanyon, 1998).
A particulate
phosphorus
submodel
(PARTLE)
for the
GLEAMS model was developed and tested by (Shirmohammadi et
aI., 1998). The submodel PARTLE provided reasonable estimates
of particulate phosphorus loss via drain tiles for a structured clay
soil in southwest Sweden. Stone et al. (1998c) used the GLEAMS
model to simulate nitrate concentrations in row crop and swine
waste spray fields in Coastal Plain watershed of North Carolina
and concluded that the model could be used to predict nitrate
loading to groundwater for similar conditions. The GLEAMS
model was applied using input data derived from GIS analysis to
show that the amount of animal waste produced in some areas of
the Tuscany valley of Italy was too much for disposal on agricultural soils with no risk to groundwater (Garnier et aI., 1998).
Alternative agricultural practices such as reducing fertilizer inputs by crediting the amount of nitrogen in irrigation water and
alfalfa were shown to reduce nitrate leaching while maintaining
crop yields in simulations using the erosion productivity calculator
(EPIC) mode] (Ramanarayanan et aI., 1998). Nitrate leaching in
sandy loam soil under no-till, reduced till, and conventional tillage
practices as predicted by the LEACHM-N and NTRM models was
within one standard deviation of observed leaching; however,
further improvements in the models are still needed partly because
of the models' inability to differentiate between tillage practices
(Dodds et aI., 1998).
A number of articles were published on the subject of various
approaches to predicting pesticide movement to ground or surface
water. Mills and Simmons (1998) used several experimental designs in both the laboratory and field to develop data on three
compounds for subsequent modeling. They concluded that PRZM
model results compared adequately to the measured results. The
fate of fenamiphos and two metabolites was measured in a field
study in the Coastal Plain of the southeastern U.S., and the data
were then compared to GLEAMS model results (Truman et aI.,
1998). The authors found that, with calibration, GLEAMS could
predict the fate of these compounds. The major route of loss was
determined to be in subsurface lateral flow. Suzuki et al. (1998)
measured 19 pesticides in soil, runoff, tile drains, and groundwater
from a golf course in Japan. They compared the field data to three
published leaching indices and to a simple laboratory assay and
found mixed results. Diaz-Diaz et a1. (1998) developed maps of
leaching potentials for four pesticides used in banana production in
the Canary Islands to rank relative risks for groundwater contamination. No verification using groundwater data was attempted.
Urban runoff water quality models are infrequently used by
managers because they are relatively costly and inaccurate (Ahyerre et aI., 1998). Examining the reasons for inaccurate predictions
from urban models, Gaume et al. (1998) used a global approach to
input parameter estimation to demonstrate that the lack of measured data and their relative redundancy cause an interaction
between parameters, which hinders calibration and prediction accuracy. However, the physically based pollutant routing over urban watershed (PROUW) model was calibrated, then used to
simulate, with reasonable accuracy, the overall runoff and pollutant generation from a 66.2-ha urban watershed in Japan (Haiping
1062
and Yamada, 1998). Osuch-Pajdzinska and Zawilski (1998a) developed a new deterministic urban runoff model and calibrated and
verified its usefulness in caleulating hydrographs and pollutographs for a 300-ha mixed industrial and residential catchment
(Osuch-Pajdzinska and Zawilski, 1998b). The macro model was
used to show that the control of pollutant runoff from urban NPS
was significant in protecting the water quality of Lake Biwa, the
largest lake in Japan (Ichiki et aI., 1998).
By applying linear regression to stormwater runoff data from an
expressway in Austin, Texas, Irish et al. (1998) determined that
processes responsible for the generation, accumulation, and
washoff of pollutants such as oil and grease and total suspended
solids were constituent specific. Observed and modeling data were
used to show that urban land surfaces rather than direct deposition
from air are the primary sources of most gasoline-related volatile
organic compounds found in urban waters (Lopes and Bender,
1998).
Lee et al. (1998) developed a steady-state model to assess the
fate of household chemicals dumped into septic systems. Model
simulations were in good agreement with observed field data for
tartrate monosuccinate, tartrate disuccinate, and orthophosphorus.
A surface-to-subsurface
two-dimensional model that employs a
streamline-equipotential
flow-net submodel was developed as a
tool for helping design trench infiltration basins (Guo, 1998).
Shukla et al. (1998) developed an attenuation factor (AP)
screening model that combines several layers of data from a GIS
to assess the vulnerability of groundwater to pesticide contamination. The AF mode] was able to identify most of the frequently
detected pesticides in an experimental watershed. Clopyralid distributions in tile drainage water simulated using the LEACHM
model were reported to be in good agreement with observed
distributions in a study conducted on irrigated land in Saskatchewan, Canada (Elliot et aI., 1998).
Hanson et al. (1998) reviewed the processes and many studies
involving the root zone water quality model (RZWQM) and concluded that the model is useful for evaluating management practices including tillage; irrigation; fertilizer, manure, and pesticide
applications; tile drainage; and crop rotations. Simulated annual
losses of atrazine from subsurface drains under cornfields using the
RZWQM were within -9.9% for modified no-till and 12.0% for
moldboard plow of observed values (Kumar et aI., 1998a). Kumar
et al. (1998b) also showed that the RZWQM was capable of
predicting nitrate leaching to a depth of 1.2 m resulting from swine
manure application with subsequent chisel plow incorporation.
Employing a rigorous stepwise evaluation procedure Thorsen et
al. (1998) demonstrated that pesticide leaching models such as
MACRO, which include a preferential flow component, passed the
validation criteria without calibration, whereas models without
preferential flow components require calibration to mimic the
influence of macropores. Using results from Iysimeters, a dynamic
pesticide leaching model that considers bypass flow in macropores
could reproduce the spatial distribution in the soil profile of two
herbicides with different sorption behaviors (Stange et al., 1998).
Kalita et al. (1998) reported that reasonable agreement was obtained between observed and predicted concentrations of atrazine
and alachlor for 3 years of study; however, in a few cases,
observed and predicted values varied widely. When site specific
inputs were used, the pesticide transport assessment (PESTRAS)
model predicted ethopos and bentazone movement in a cropped
field with sandy soils within the 95% confidence intervals of the
observed data (Tiktak et aI., 1998).
Monitoring. Strecker (1998) suggested that U.S. EPA-funded
Water Environment
Research,
Volume 71, Number 5
Fate and Effects of Pollutants
BMP effectiveness
studies utilize standard data collection, report-
ing, and analysis methods. For example, he suggested including a
standard list of pollutants (TSS, BOD, COD, TP, SP, TKN, N02 +
N03, copper, lead, and zinc), verifying flow measurements and
composite techniques, measuring appropriate watershed and hydrology variables, reporting concentration as event mean concentrations (EMC), and calculating BMP efficiency as a comparison
between the average EMCs between the inflows and outflows.
Field methods to measure hydrologic conditions were examined.
A modified drop-box weir was tested for suitability in sedimentladen flow measurements for small watershed and plot studies
(Bonta, 1998). Fankhauser (1998) demonstrated that the size of a
tipping bucket rain gauge is not a large source of measurement
error but that a precise static calibration is important for accurate
rainfall measurements. Monitoring discharge and collecting flowweighted water samples at multiple runoff plots was accomplished
by a distributed data acquisition system controlled by a host
computer, eliminating the need for multiple data loggers (Burcham
et aI., 1998).
Johnson (1998) successfully measured instream turbidity in both
the low and high turbidity ranges with a laser-based reflectometer.
Edwards (1998) developed a sensor for a combined test of color
and turbidity. The number of purge cycles required to obtain a
representative well sample for pesticide analysis varied as a function of local recharge area, but a minimum of one purge cycle was
required (Novak and Watts, 1998b).
Kotlash and Chessman (1998) determined that changes in measured concentrations of nitrogen and phosphorus occur if water
quality samples are left without preservation (refrigeration or acidification) for more than 2 days. In contrast, Allen-Diaz et al. (1998)
demonstrated that water quality samples collected in remote watershed studies can be stored un refrigerated for a week (e.g., in
automatic samplers) and refrigerated for up to 1 month without
acid preservation and still allow for accurate measurements of
nitrate, orthophosphate, pH, and conductivity.
Lab analysis procedures related to monitoring were examined. A
new method for measuring low concentrations of ammonia was
tested (Meredith et aI., 1998). Alonso et al. (1998) demonstrated
similar fecal and E. coli coliforms detection levels using a new
medium, Chromocult Colifrom agar, as compared with the standard methods membrane filtration fecal coliform medium; however, lowering the incubation temperature from 44.5 to 41 °C was
thought to minimize false negatives for some metabolically injured
fecal coliforms. Immunoassays were successful as a screening tool
for atrazine levels of 0.02 I1glL for water samples and 0.005 I1g1kg
for soil samples (Amin et aI., 1998).
Several authors discussed appropriate statistical analysis of water quality data. For analysis of censored data (below detection
limit), Clarke (1998) demonstrated that substitution of a constant,
such as one-half the detection limit, for nondetect data was the best
method for small sample size comparisons, even with a high
percentage of nondetects. Parkhurst and Stern '(1998) demonstrated
that taking the average of the actual sample counts, including
zeros, and then weighting by sample volume provided the best
estimate of upper confidence limits for the true average concentrations of Cryptosporidium.
Hamed and Rao (1998) presented a modified Mann-Kendall
trend test that adjusts the variance of the test statistic for the effect
of autocorrelation and therefore is valid in a hydrologic time series.
Monthly data over a lO-year timeframe was a sufficient sample
frequency to detect a trend greater than 15% of the variance using
Literature Review 1999
a seasonal Mann-Kendall
test modified to account for autocorre-
lation (Thas et al., 1998).
D.E. Line, G.D. Jennings, R.A. McLaughlin, D.L Osmond, W.A.
Harman, L.A. Lombardo, K.L. Tweedy, and J. Spooner are part of
the North Carolina Cooperative Extension Service at North Carolina State University. Correspondence should be addressed to Dan
Line, Box 7637, North Carolina State University, Raleigh, NC
27695-7637.
REFERENCES
Aase, J.K.; Bjomeberg, D.L.; and Sojka, R.E. (1998) Sprinkler Irrigation
Runoff and Erosion Control with Polyacrylamide-Laboratory Tests.
Soil Sci. Soc. Am. J., 62, 1681.
Abu-Ashour, J.; Joy, D.M.; Lee, H.; Whiteley, H.R.; and Zelin, S. (1998)
Movement of Bacteria in Unsaturated Soil Columns with Macropores.
Trans. Am. Soc. Agric. Eng., 41, 1043.
Ahn, H. (1998) Estimating the Mean and Variance of Censored Phosphorus
Concentrations in Rorida Rainfall. J. Am. Water Resour. Assoc., 34,
583.
Ahyerre, M.; Chebbo, G.; Tassin, B.; and Gaume, E. (1998) Storm Water
Quality Modeling, an Ambitious Objective? Water Sci. Techno/.
(G.B.), 37, 205.
Akhtar, S.; Misbahuddin, P.; Siddique, P.M.H.; and Baloch, U.K. (1998)
Effect of Neem Cake on Persistence of Diazinon and Endosulfan in
Paddy Soil. Pestic. Sci., 52,218.
Allen-Diaz, B.; Hammerling, E.; and Campbell, C. (1998) Comparison of
Standard Water Quality Sampling with Simpler Procedures. J. Soil
Water Conserv., 53, 42.
AI-Mihanna, A.A.; Salama, A.K.; and Abdalla, M.Y. (1998) Biodegradation of Chloropyrifos by Either Single or Combined Cultures of Some
Soilborne Plant Pathogenic Fungi. J. Environ. Sci. Health, 833, 693.
Alonso, J.L.; Soriana, A.; Amoros, I.; and Ferrus, M.A. (1998) Quantitative
Determination of E. Coli and Fecal Coliforms in Water Using a
Chromogenic Medium. J. Environ. Sci. Health, A33, 1229.
Amatya, D.M.; Gilliam, J.W.; Skaggs, R.W.; Lebo, M.E.; and Campbell,
R.G. (1998) Effects of Controlled Drainage on Forest Water Qua]ity.
J. Environ. Qual., 27, 923.
Amin, M.R.; Malek, M.A.; Rahman, M.; and Hoque, E. (1998) Enzyme
Immunoassay for Atrazine Analysis in Water and Soil. Pestic. Sci..
52, 152.
Arthur, M.A.; Coltharp, G.B.; and Brown, D.L. (1998) Effec~s of Best
Management Practices on Forest Streamwater Quality in Eastern
Kentucky. J. Am. Water Resour. Assoc., 34,481.
Atkinson, J.F.; Gupta, S.K.; DePinto, J.V.; and Rumer, R.R. (1998) Linking Hydrodynamic and Water Quality Models with Different Scales.
J. Environ. Eng., 124, 399.
Baffaut, C.; Nearing, M.A.; and Govers, G. (1998) Statistical Distributions
of Soil Loss from Runoff Plots and WEPP Model Simulations. Soil
Sci. Soc. Am. J., 62, 756.
Barifield, B.I.; Blevins, R.L.; Fogle, A.W.; Madison, C.E.; Inamdar, S.;
Carey, D.1.; and Evangelou, V.P. (1998) Water Quality Impacts of
Natural Filter Strips in Karst Areas. Trans. Am. Soc. Agric. Eng.. 41,
371.
Barrett, M.E.; Malina, J.F.; and Charbeneau, R.I. (l998a) An Evaluation of
Geotextiles for Temporary Sediment Control. Water Environ. Res..
70,283.
Barrett, M.E.; Walsh, P.M.; Malina, J.F.; and Charbeneau. R.J. (1998b)
Performance of Vegetative Controls for Treating Highway Runoff. J.
Environ. Eng., 124, 1121.
Barrett, M.E.; Irish, L.B.; Malina, J.P.; and Charbeneau, R.I. (1998c)
Characterization of Highway Runoff in Austin, Texas, Area. J. Environ. Eng., 124, ]31.
Battaglin, W.A., and Goolsby, D.A. (1998) Regression Models of Herbicide Concentrations in Outflow from Reservoirs in the Midwestern
USA, 1992. J. Am. Water Resour. Assoc., 34, 1369.
1063
Fate and Effects of Pollutants
Bengtson,
R.L.; Selim, H.M.; and Ricaud, R. (1998) Water Quality from
Sugarcane Production on Alluvial Soils. Trans. Am. Soc. Agric. Eng.,
41, 1331.
Bernard, e.; Mabit, L.; Wicherek,
S.;
and Laverdiere,
M.R. (1998) Long-
Term Soil Redistribution in a Small French Watershed
from Cesium-137 Data. J. Environ. Qual., 27, 1178.
Bertrand-Krajewski,
D.L.; Karlen, D.L.; Kanwar,
(1998) Alternative
N Fertilizer
Strategies
of
and the First
e.A.
Effects on
Subsurface Drain Effluent and N Uptake. Appl. Eng. Agric., 14,469.
Boardman, J. (1998) An Average Soil Erosion Rate for Europe: Myth or
Reality? J. Soil Waler Conserv., 53, 46.
Bonta, J.V. (1998) Modified Drop-Box Weir for Monitoring
M. (1998) Transport and Persistence of Pesticides in Alluvial Soils:
r.
Simazine. J. Environ. Qual., 27,543.
Usage to the Occurrence
L.R. (1998) Relation of
of Cotton and Rice Herbicides
in Three
Streams the Mississippi Delta. Environ. Sci. Technol., 32, 3673.
Coyne, M.S.; Gilfillen, R.A.; Villalba,
R.S.; and Cambardella,
Management
Cogger, C.G.; Bristow, P.R.; Stark, J.D.; Getzin, L.W.; and Montgomery,
Coupe, R.H.; Thurman, E.M.; and Zimmerman,
J.; Chebbo, G.; and Saget, A. (1998) Distribution
Pollutant Mass vs. Volume in Storm water Discharges
Flush Phenomenon. Water Res. (G.B.), 32, 2341.
Bjorneberg,
as Estimated
M. (1998) Transport and Persistence of Pesticides in Alluvial Soils: II.
Carbofuran. J. Environ. Qual., 27,551.
A.; Rhodes,
R.; Dunn, L.; and
Blevins, R.L. (1998) Fecal Bacteria Trapping by Grass Filter Strips
During Simulated Rain. J. Soil Waler Conserv., 53, 140.
Daniel, T.C.; Sharpley,
A.N.; and Lemunyon,
Phosphorus and Eutrophication:
J.L. (1998) Agricultural
A Symposium Overview. J. Environ.
Qua/., 27,251.
Flows from
D'Arcy, BJ.; Usman, F.; Griffiths, D.; and Chatfield, P. (1998) Initiatives
Trans. Am. Soc. Agric. Eng., 41,
To Tackle Diffuse Pollution in the U.K. Waler Sci. Technol. (G.B.),
Borden, R.e.; Dorn, J.L.; Stillman, J.B.; and Liehr, S.K. (1998) Effect of
Davis, J.R.; Farley, T.F.N.; Young, W.J.; and Cuddy, S.M. (1998) The
Erosion Plots and Small Watersheds.
565.
38, 131.
In-Lake Water Quality on Pollutant Removal in Two Ponds. J. Envi·
ron. Eng., 124,737.
Brannan, K., and Hamlett,
J.M. (1998) Using Geostatistics
To Select
Grid-Cell Layouts for the AGNPS Model. Trans. Am. Soc. Agric.
Eng., 41, 1011.
Bridoux, G.A.; Villeroux, A.; Riotte, M.; and Huau, M.C. (1998) Optimized Lamellae Settling Process for Run Off Water Treatment. Waler
Sci. Technol. (G.B.), 38, 107.
Brown, MJ.; Robbins, C.W.; and Freeborn, L.L. (1998) Combining Cottage Cheese Whey and Straw Reduces Erosion While Increasing
Infiltration in Furrow Irrigation. J. Soil Waler Conserv., 53, 152.
Bucheli, T.D.; Muller, S.R.; Voegelin, A.; and Schwarzenbach, R.P. (1998)
Bituminous Roof Sealing Membranes as Major Sources of the Herbicide (R,S)-Mecoprop
tion of Groundwater
in Roof Runoff Waters: Potential Contaminaand Surface Waters. Environ. Sci. Technol., 32,
3465.
Burcham, T.N.; Wren, D.G.; Wooten, J.R.; and Varco, J.J. (1998) Distributed Data Acquisition
System for Runoff Monitoring and Automated
Water Sampler Control. App/. Eng. Agric., 14, 591.
Burckhardt, J.e., and Todd, B.L. (1998) Riparian Forest Effect on Lateral
Stream Channel Migration in the Glacial Till Plains. 1. Am. Water
Resour. Assoc., 34, 179.
Cassell, E.A.; Dorioz, J.M.; Kort, R.L.; Hoffmann, J.P.; Meals, D.W.;
Kirschtel, D.; and Braun, D.e. (1998) Modeling Phosphorus Dynamics in Ecosystems: Mass Balance and Dynamic Simulation Approa~hes. J. Environ. Qual., 27, 293.
Chandler, D.G .. and Walter, M.F. (1998) Runoff Responses Among Common Land Uses in the Uplands of Mata]om, Leyte, Philippines. Trans.
Am. Soc. Agric. Eng., 41, ]635.
Chen, Y.D.; Carse], R.F.; McCutcheon, e.; and Nutter, W.L. (1998a)
Stream Temperature Simulation of Forested Riparian Areas: 1. Watershed-Scale Model Development. J. Environ. Eng., 124, 304.
Chen, Y.D.; McCutcheon, C.; Norton, DJ.; and Nutter, W.L. (1998b)
Stream Temperature Simulation of Forested Riparian Areas: II. Model
Application. J. Environ. Eng., 124, 316.
Chong, S.K.; Klubek, B.P.; and Weber, J.T. (1998) Herbicide Contamination by the ] 993 Great Flood Along the Mississippi River. J. Am.
Water Resour. Assoc., 34,687.
Christen, K. (1998a) Stricter Regulations Inevitable for Livestock Industry.
Ind. Wastewater, 6,3, 7.
Christen, K. (I 998b) Pennsylvania's Nutrient Management Act Takes Lead
in Controlling Farm Runoff. Water Environ. Techno/., 10, 22.
Claassen, R.; Heimlich, R.E.; House, R.M.; and Wiebe, K.D. (1998)
Estimating the Effects of Relaxing Agricultura] Land Use Restrictions: Wetland Delineation in the Swampbuster Program. Rev. Agric.
Econ., 20, 390.
Clarke, J.U. (1998) Evaluation of Censored Data Methods To Allow
Statistical Comparison Among Very Small Samples with Below Detection Limit Observations. Environ. Sci. Techno/., 32, 177.
Cogger, e.G.; Stark, J.D.; Bristow, P.R.; Getzin, L.W.; and Montgomery,
1064
Experience
of Using a Decision Support System for Nutrient Man-
agement in Australia. Water Sci. Techno/. (G.B.), 37, 209.
deHoop, C.F.; Einsel, D.A.; Ro, K.S.; Chen, S.; Gibson, M.D.; and
Grozdits, G.A. (1998) Stormwater Runoff Quality of a Louisiana Log
Storage and Handling Facility. J. Environ. Sci. Health, A33, 165.
Deletic, A. (1998) The First Flush Load of Urban Surface Runoff. Water
Res. (G.B.), 32, 2462.
Deletic, A.B., and Maksimovic, e.T. (1998) Evaluation of Water Quality
Factors in Storm Runoff from Paved Areas. J. Environ. Eng., 124,
869.
De]gado, J.A.; Shaffer, M.; and Brodahl, M.K. (]998a) New NLEAP for
Shallow and Deep Rooted Rotations. J. Soil Water Conserv., 53, 338.
De]gado, J.A.; Follett, R.F.; Sharkoff, J.L.; Brodahl, M.K.; and Shaffer,
M.J. (l998b)
NLEAP
Facts About Nitrogen
Management.
J. Soil
Waler Conserv., 53, 332.
Delong, M.D., and Brusven, M.A. (1998) Macroinvertebrate
Structure Along the Longitudina]
Community
Gradient of an Agriculturally
Im-
pacted Stream. Environ. Manage., 22, 445.
Deluca, T.H.; Patterson, W.A., IV; Freimund, W.A.; and Cole, D.N. (1998)
Influence of Llamas, Horses, and Hikers on Soil Erosion from Established Recreation
Trials in Western Montana, USA. Environ. Man-
age., 22, 255.
Diaz-Diaz, R.; Garcia-Hernandez,
J.E.;.and
Loague, K. (1998) Leaching
Potentials of Four Pesticides Used for Bananas in the Canary Islands.
J. Environ. Qual., 27, 562.
Dodds, G.T.; Madramootoo, e.A.; and Serem, V.K. (1998) Predicting
Nitrate-N
Leaching
Under Different
Tillage
Systems
Using
LEACHM and NTRM. Trans. Am. Soc. Agric. Eng., 41, ]025.
Dona]d, W.W.; Hjelmfelt, A.T., Jr.; and A]berts,
Distribution and Variability Across Goodwater
tral Missouri. J. Environ. Qual., 27, 999.
Douglas, C.L.; King, K.A.; and Zuzel, J.F. (1998)
rus in Surface Runoff and Sediment from a
E.E. (1998) Herbicide
Creek Watershed CenNitrogen and PhosphoWheat-Pea Rotation in
Northeastern Oregon. J. Environ. Qual., 27, 1170.
Dunne, T. (1998) Critical Data Requirements for Prediction of Erosion and
Sedimentation in Mountain Drainage Basins. J. Am. Water Resour.
Assoc., 34, 795.
Ebbert, J.C., and Kim, M.H. (1998) Relation Between Irrigation Methods,
Sediment Yields, and Losses of Pesticides and Nitrogen. J. Enviroll.
Qua/., 27,372.
Edwards, H.O. (1998) An Instrument for the Measurement of Color and
Turbidity in Natural Waters. Water Sci. Technol. (G.B.), 37, 263.
Eigenberg, R.A.; Kortha]s, R.L.; Nienaber, J.A.; and Hahn, G.L. (1998)
Implementation of a Mass Balance Approach to Predicting Nutrient
Fate of Manure from Beef Cattle Feedlots. Appl. Eng. Agric., 14,475.
E]-Dib, M.A., and Abou-Waly, H.F. (1998) Biodegradation of Some Triazines and Phenylureas in Surface Waters. Water Res. (G.B.), 32, 1881.
Elliott, J.A.; Cessna, AJ.; Best, K.B.; Nicholaichuk, W.; and Tollefson,
L.C. (1998) Leaching and Preferential F]ow of Clopyralid Under
Water Environment Research, Volume 71, Number 5
Fate and Effects of Pollutants
Irrigation:
Field Observations
Modeling. J. Environ.
and Simulation
Qual., 27, 124.
Ertl, D.S.; Young, K.A.; and Raboy, V. (1998) Plant Genetic Approaches
to Phosphorus
Management
in Agricultural
Qual., 27, 299.
Evans, J.R.; Edwards, D.R.; Workman,
Production.
J. Environ.
F.S.; Karns,
R.M. (1998)
J.S.; and Torrents,
A. (1998)
Degradation
of
Atrazine in Soil by Streptomyces. J. Environ. Sci. Health, B33, 37.
Falconer, K.E. (1998) Managing Diffuse Environmental Contamination
from Agricultural
Pesticides: An Economic Perspective on Issues and
Policy Options, with Particular Reference to Europe. Agric. Ecosyst.
Environ., 69, 37.
Fankhauser,
R. (1998) Influence of Systematic Errors from Tipping Bucket
Rain Gauges on Recorded Rainfall Data. Water Sci. Technol. (G.B.),
37, 121.
Farenhorst,
A., and Bowman,
Atrazine and Metolachlor
Fenelon,
B.T. (1998)
Competitive
Sorption
of
in Soil. J. Environ. Sci. Health, B33, 671.
J.M., and Moore, R.C. (1998) Transport
of Agrichemicals
Ground and Surface Water in a Small Central Indiana Watershed.
Environ. Qual., 27, 884.
Field, R.; Borst, M.; O'Connor,
to
J.
T.P.; Stinson, M.K.; Fan, C.Y.; Perdek,
J.M.; and Sullivan, D. (1998) Urban Wet Weather Flow Management:
Research Directions. J. Water Resour. Plann. Manage., 124, 168.
Forster, J. (1998) The Influence of Location and Season on the Concentrations of Macroions and Organic Trace Pollutants in Roof Runoff.
Water Sci. Technol. (G.B.), 38, 3.
Franti, T.G.; Peter, C.J.; Tierney, D.P.; Fawcett, R.S.; and Myers, S.A.
(1998) Reducing Herbicide Losses from Tile-Outlet Terraces. J. Soil
Water Conserv., 53, 25.
Fraser, R.H.; Barten, P.K.; and Pinney, D.A.K. (1998) Predicting Stream
Pathogen Loading from Livestock Using a Geographical Infonnation
System-Based Delivery Model. J. Environ. Qual., 27, 935.
Frick, A.; Zebarth, B.J.; and Szeto, S.Y. (1998) Behavior of the Soil
Fumigant Methyl Isothiocyanate in Repacked Soil Columns. J. Environ. Qual., 27, 1158.
Gachter, R.; Ngatiah, J.M.; and Stamm, C. (1998) Transport of Phosphate
from Soil to Surface Waters by Preferential Flow. Environ. Sci.
Technol., 32, 1865.
Gallichand, J.; Aubin, E.; Baril, P.; and Debailleul,
G. (1998) Water
Quality Improvement at the Watershed Scale in an Animal Production
Area. Can. Agric. Eng., 40, 67.
Galya, D.; Mitchell, D.; and Gerath, M. (1998) Watershed-Based Pennitting: Wave of the Future of Water Quality Management. Environ.
Regulation Permitting, Summer 98.
Garnier, M.; Porto, A.L.; Marini, R.; and Leone, A. (1998) Integrated Use
of GLEAMS and GIS To Prevent Groundwater Pollution Caused by
Agricultural Disposal of Animal Waste. Environ. Manage., 22, 747.
Gascho, G.J.; Wauchope, R.D.; Davis, J.G.; Truman, C.C.; Dowler, C.C.;
Hook, lE.; Sumner, H.R.; and Johnson, A.W. (1998) Nitrate-Nitrogen, Soluble, and Bioavailable Phosphorus Runoff from Simulated
Rainfall After Fertilizer Application. Soil Sci. Soc. Amer. J., 62, 171 I.
Gaume, E.; Villeneuve, J.-P.; and Desbordes, M. (1998) Uncertainty Assessment and Analysis of the Calibrated Parameter Values of an
Urban Storm Water Quality Model. J. Hydrol. (Neth.), 210, 38.
Gburek, W.J., and Sharpley, A.N. (1998) Hydrologic Controls on Phosphorus Loss from Upland Agricultural Watersheds. J. Environ. Qual.,
27,267.
Gennari, M.; Negre, M.; and Vindrola, D. (1998) Adsorption of the
Herbicides Imazapyr, Imazethapyr and Imazaquin on Soils and Humic
Acid. J. Environ. Sci. Health, B33, 547.
Gerdes, P., and Kunst, S. (1998) Bioavailability of Phosphorus as a Tool
for Efficient Reduction Schemes. Water. Sci. Technol. (G.B.), 37, 241.
Ghidey, F., and Alberts, E.E. (1998) Runoff and Soil Losses as Affected by
Corn and Soybean Tillage Systems. J. Soil Water Conserv., 53, 64.
Gilley, J.E., and Eghball, B. (1998) Runoff and Erosion Following Field
Literature Review 1999
of Beef Cattle Manure and Compost.
Trans. Am. Soc.
97.
S.R.; and Williams,
Response of Runoff Diazinon Concentration to Formulation and PostApplication Irrigation. Trans. Am. Soc. Agric. Eng., 41, 1323.
Fadullon,
Application
Agric. Eng., 41, 1289.
Gilley, J.E., and Doran, J.W. (1998) Soil Erosion Potential of Former
Conservation Reserve Program Sites. Trans. Am. Soc. Agric. Eng., 41,
Ginting, D.; Moncrief, J.F.; Gupta, S.c.; and Evans, S.D. (1998a) Corn
Yield, Runoff, and Sediment Losses from Manure and Tillage Systems. J. Environ. Qual., 27, 1396.
Ginting, D.; Moncrief, J.F.; Gupta, S.C.; and Evans, S.D. (l998b) Interaction Between Manure and Tillage System on Phosphorus Uptake
and Runoff. J. Environ. Qual., 27, 1403.
Gold, A.J.; Jacintlle, P.A.; Groffman, P.M.; Wright, W.R.; and Puffer, R.H.
(1998) Patchiness in Groundwater Nitrate Removal in a Riparian
Forest. J. Environ. Qual., 27, 146.
Goss, M.J.; Barry, D.A.J.; and Rudolph, D.L. (1998) Contamination in
Ontario Farmstead Domestic Wells and Its Association
with Agricul-
ture: 1. Results from Drinking Water Wells. J. Contam. Hydrol., 32,
267.
Govindaraju,
R.S. (1998) Effective
Erosion
Parameters
for Slopes with
Spatially Varying Properties. J. [rrig. Drain. Eng., 124,81.
Grace, J.M.; Rummer, B.; Stokes, B.J.; and Wilhoit, J. (199&) Evaluation
of Erosion
Control Technique's
on Forest Roads. Trans. Am. Soc.
Agric. Eng., 41, 383.
Green, D.M. (1998) Recreational Impacts on Erosion and Runoff in a
Central Arizona Riparian Area. J. Soil Water Conserv., 53, 38.
Grove, G.; Szeto, S.Y.; Liebscher, H.; Hii, B.; and Zebarth, B.J. (1998a)
Occurrence of 1,2-Dichloropropane
and 1,3-Dichloropropene
in the
Abbotsford Aquifer, British Columbia. Water Qual. Res. J. Can., 33,
51.
Grove, M.; Harbor, J.; and Engel, B. (l998b) Composite vs. Distributed
Curve Numbers: Effects on Estimates of Storm Runoff Depths. J. Am.
Water Resour. Assoc., 34, 1015.
Guo, J.C.Y. (1998) Surface-Subsurface
Model for Trench Infiltration Basins. J. Water Resour. Plann. Manage., 124, 280.
Ha, S.R.; Jung, DJ.; and Yoon, C.H. (1998) A Renovated Model for
Spatial Analysis of Pollutant Runoff Loads in Agricultural Watershed.
Water Sci. Technol. (G.B.), 38, 207.
Haiping, Z., and Yamada, K. (1998) Simulation of Nonpoint Source
Pollutant Loadings from Urban Area During Rainfall: An Application
of a Physically-Based Distributed Model. Water Sci. Technol. (G.B.),
38, 199.
Hamed, K.H., and Rao, A.R. (1998) A Modified Mann-Kendall Trend Test
for Autocorrelated Data. J. Hydrol. (Neth.), 204, 182.
Hanson, J.D.; Ahuja, L.R.; Shaffer, M.D.; Rojas, K.W.; DeCoursey, D.G.;
Farahani, H.; and Johnson, K. (1998) RZWQM: Simulating the Effects of Management on Water Quality and Crop Production. Agric.
Syst., 57, 161.
Hawkins, G.L.; Hill, D.T.; Rochester, E.W.; and Wood, C.W. (1998)
Evaluation of Vegetative Filter Strips for Swine Lagoon Wastewater.
Trans. Am. Soc. Agric. Eng., 41, 639.
Heng, H.H., and Nikolaidis, N.P. (1998) Modeling of Nonpoint Source
Pollution of Nitrogen at the Watershed Scale. J. Am. Water Resour.
Assoc., 34, 359.
Herlihy, A.T.; Stoddard, J.L.; and Johnson, C.B. (1998) The Relationship
Between Stream Chemistry and Watershed Land Cover Data in the
Mid-Atlantic Region, U.S. Water, Air, Soil Pol/ut. (Neth.), 105,377.
Hill, D.T., and Payton, J.D. (1998) Influence of Temperature on Treatment
Efficiency of Constructed Wetlands. Trans. Am. Soc. Agric. Eng., 41,
393.
Hill, V.R., and Sobsey, M.D. (1998) Microbial Indicator Reductions in
Alternative Treatment Systems for Swine Wastewater. Water Sci.
Technol. (G.B.), 38, 119.
Hu, M.Q., and Brusseau, M.L. (1998) Coupled Effects of Nonlinear,
Rate-Limited Sorption and Biodegradation on Transport of 2A-Dichlorophenoxyacetic
Acid in Soil. Environ. Toxicol. Chem., 17, 1673.
Huang, C.-H. (1998) Sediment Regimes Under Different Slope and Surface
Hydrologic Conditions. Soil Sci. Soc. Am. J., 62, 423.
Hubbard, R.K.; Newton, G.L.; Davis, J.G.; Lowrance, R.; Vellidis, G.; and
1065
Fate and Effects of Pollutants
Dove, e.R. (1998) Nitrogen Assimilation
Receiving Swine Lagoon Wastewater.
41, 1295.
by Riparian Buffer Systems
Trans. Am. Soc. Agric. Eng.,
Hun, T. (1998) Costs, Nonpoint Sources Are Top TMDL Concerns. Water
Environ. Technol., 10, 36.
Ichiki, A.; Ohnishi, T.; and Yamada,
K. (1998)
Estimation
of Urban
Nonpoint Source Pollution in Lake Biwa Basin. Water Sci. Technol.
(G.B.), 38, 157.
Ingersoll, T.L., and Baker, L.A. (1998) Nitrate Removal in Wetland Mi-
Atrazine Transport to Subsurface Drains. Trans. Am. Soc. Agric. Eng.,
41,627.
Kumar, A.; Kanwar, R.S.; and Ahuja, L.R. (l998b)
of Nitrate
Concentrations
in Subsurface
RZWQM Simulation
Drainage
from Manured
Plots. Trans. Am. Soc. Agric. Eng., 41, 587.
Laine, S.; Poujol, T.; Dufay, S.; Baron, J.; and Robert, P. (1998) Treatment
of Stormwater to Bathing Water Quality by Dissolved Air Flotation,
Filtration and Ultraviolet Disinfection.
Water Sci. Techno/. (G.B.), 38,
99.
crocosms. Water Res. (G.B.), 32, 677.
Iragavarapu, T.K.; Posner, J.L.; and Bubenzer, G.D. (1998) The Effect of
Various Crops on Bromide Leaching to Shallow Groundwater Under
Natural Rainfall Conditions. J. Soil Water Conserv., 53, 146.
Irish, L.B.; Barrett, M.E.; Malina, J.F.; and Charbeneau, R.I. (1998) Use of
Lane, L.J.; Hernandez, M.; and Nichols, M. (1998) Processes Controlling
Regression Models for Analyzing Highway Storm-Water Loads. J.
Environ. Eng., 124, 987.
Jabro, J.D.; Stout, W.L.; Fales, S.L.; and Fox, R.H. (1998) Evaluation of
NCSW AP Model Using Nitrate-Leaching
Data from Soil Core Ly-
on the D~gradation of 2,4-D During Transport. Environ. Sci. Techno/.,
simeters. J. Environ. Qua/., 27, 390.
Jacinthe, P.-A.; Groffman, P.M.; Gold, A.1.; and Mosier, A. (1998) Patchiness in Microbial Nitrogen Transformations
in Groundwater in a
Riparian Forest. J. Environ. Qual., 27, 156.
Jebellie, S.1., and Prasher, S.O. (1998) Role of Water Table Management
in Reducing Metribuzin Pollution. Trans. Am. Soc. Agric. Eng., 41,
1051.
Jensen, M.B.; Hansen, H.e.B.; Hansen, S.; Jorgensen, P.R.; Magid, J.; and
Nielsen, N.E. (1998) Phosphate and Tritium Transport Through Undisturbed Subsoil as Affected by Ionic Strength. J. Environ. Qua/., 27,
139.
Johnson, M. (1998) Remove Turbidity Measurement with a Laser Reftectometer. Water Sci. Technol. (G.B.), 37, 255.
Johnson, R.M., and Sims, J.T. (1998) Sorption of Atrazine and Dicamba in
Delaware Coastal Plain Soils: A Comparison
Batch Equilibrium
of Soil Thin Layer and
Results. Pes/ic. Sci., 54,91.
Joy, D.M.; Lee, H.; Reaume, C.M.; Whiteley, H.R.; and Zelin, S. (1998)
Microbial
Contamination
Field Applications
Juracek,
K.E. (1998)
of Subsurface
Tile Drainage Water from
of Liquid Manure. Can. Agric. Eng., 40, 153.
Analysis
Historical Nonpoint-Source
Assoc., 34, 1449.
of Lake-Bottom
Sediment
To Estimate
Phosphorus Loads. J. Am. Water Resour.
Kalita, P.K.; Ward, A.D.; Kanwar, R.S.; and McCool, D.K. (1998) Simulation of Pesticide Concentrations in Groundwater Using Agricultural
Drainage and Pesticide Transport (ADAPT) Model. Agric. Water
Manage., 36, 23.
Kaluli, J.W.; Madramootoo, C.A.; and Djebbar, Y. (1998) Modeling Nitrate Leaching Using Meural Networks. Waler Sci. Technol. (G.B.),
38,127.
Katers, J.F., and Zanoni, A.E. (1998) Nitrogen Removal. Water Environ.
Techno/ .. 10, 32.
Kim, J.-H., and Feagley, S.E. (1998) Adsorption and Leaching of Trifluralin, Metholachlor, and Metribuzin in a Commerce Soil. J. Environ.
Sci. Health. 833, 529.
Kinnel, P.LA., and Risse, L.M. (1998) USLE-M: Empirical Modeling
Rainfall Erosion Through Runoff and Sediment Concentration. Soil
Sci. Soc. Am. J., 62, 1667.
Kolpin, D.W.; Barbash, J.E.; and Gilliom, R.J. (1998a) Occurrence of
Pesticides in Shallow Groundwater of the United States: Initial Results from the National Water-Quality Assessment Program. Environ.
Sci. Technol., 32, 558.
Kolpin, D.W.; Thurman, E.M.; and Linhart, S.M. (l998b) The Environmental Occurrence of Herbicides: The Importance of Degradates in
Ground Water. Arch. Environ. Con/am. Toxicol., 35, 385.
Kotlash, A.R., and Chessman, B.C. (1998) Effects of Water Sample Preservation and Storage on Nitrogen and Phosphorus Determinations:
Implications for the Use of Automated Sampling Equipment. Water
Res. (G.B.), 32, 373\.
Kumar, A.; Kanwar, R.S.; and Ahuja, L.R. (1998a) Evaluation of Preferential Flow Component of RZWQM in Simulating Water and
1066
Sediment Yield from Watersheds
as Functions of Spatial Scale. En-
viron. Model Software, 12, 355.
Langner, H.W.; Inskeep, W.P.; Gaber, H.M.; Jones, W.L.; Das, B.S.; and
Wraith, J.M. (1998) Pore Water Velocity and Residence Time Effects
32, 1308.
Lapp, P.; Madramootoo, C.A.; Enright, P.; Papineau, F.; and Perrone, J.
(1998) Water Quality of an Intensive Agricultural Watershed in
Quebec. J. Am Water Resour. Assoc., 34,427.
Larsen, T.; Broch, K.; and Andersen, M.R. (1998) First Flush Effects in an
Urban Catchment
Area in Aalborg.
Water Sci. Techno/. (G.B.), 37,
251.
Lebo, M.E., and Herrmann, R.B. (1998) Harvest Impacts on Forest Outflow in Coastal North Carolina. J. Environ. Qua/., 27, 1382.
Leeming, R.; Bate, N.; Hewlett, R.; and Nichols, P.D. (1998) Discriminating Faecal Pollution: A Case Study of Stormwater Entering Port
Phillip Bay, Australia. Water Sci. Technol. (G.B.), 38, 15.
Lee, L.K. (1998) Groundwater
Quality and Farm Income: What Have We
Learned? Rev. Agric. Econ., 20, 168.
Lee, S.; McAvoy, D.C.; Szydlik, J.; and Schnoor, J.L. (1998) Modeling the
Fate and Transport
Groundwater,
of Household
Chemicals
Lennox, S.D.; Foy, R.H.; Smith, R.V.; Unsworth,
(1998) A Comparison
Northern
in Septic
Systems.
36, 123.
Ireland
of Agricultural
E.F.; and Smyth, D.R.
Water Pollution
with Those in England
and Wales.
Incidents in
Water Res.
(G.B.), 32, 649.
Lentz, R.D.; Sojka, R.E.; and Robbins, C.W. (1998) Reducing Phosphorus
Losses from Surface-Irrigated
Fields: Emerging Polyacrylamide
Technology. J. Environ. Qual., 27, 305.
Lerch, R.N.; Blanchard, P.E.; and Thurman, E.M. (1998) Contribution of
Hydroxylated Atrazine Degradation Products to the Total Atrazine
Load in Midwestern Streams. Environ. Sci. Technol., 32, 40.
Letson, D., and Gollehon, N. (1998) Spatial Economics of Targeting
Manure Policy. J. Am. Water Resour. Assoc., 34, 185.
Lim, T.T.; Edwards, D.R.; Workman,
S.R.; Larson, B.T.; and Dunn, L.
(1998) Vegetated Filter Strips Removal of Cattle Manure Constituents
in Runoff. Trans. Am. Soc. Agric. Eng., 41, 1375.
Lindenschmidt, K.E.; Suhr, M.; Magumba, M.K.; Hecky, R.E.; and Bugenyi, F.W.B. (1998) Loading of Solute and Suspended Solids from
Rural Catchment Areas Flowing into Lake Victoria in Uganda. Water
Res. (G.B.), 32, 2776.
Lindley, M.R.; Barfield, B.1.; Ascough, J.e.; Wilson, B.N.; and Stevens,
E.W. (l998a) Hydraulic Simulation Techniques Incorporated in the
Surface Impoundment Element of WEPP. App/. Eng. Agric., 14, 249.
Lindley, M.R.; Barfield, B.1.; Ascough, J.e., II; Wilson, B.N.; and Stevens,
E.W. (1998b) The Surface Impoundment Element for WEPP. Trans.
Am. Soc. Agric. Eng., 41, 555.
Line, D.E.; Harman, W.A.; and Jennings, G.D. (1998) Comparing Sampling Schemes for Monitoring Pollutant Export from a Dairy Pasture.
J. Am. Water Resour. Assoc., 34, 1265.
Lisle, LG.; Rose, C.W.; Hogarth, W.L.; Hairsine, P.B.; Sander, G.e.; and
Parlange, J.-Y. (1998) Stochastic Sediment Transport in Soil Erosion.
J. Hydrol. (Neth.), 204, 217.
Liu, D.; Maguire. R.I.; Lau, Y.L.; Pacepavicius, G.1.; Okamura, H.; and
Aoyama, 1. (1998) Microbial Adsorption of Cyanazine and Metolachlor. J. Environ. Sci. Health, 833, I.
Livingston, M.L., and Cory, D.C. (1998) Agricultural
Nitrate Contamina-
Water Environment Research, Volume 71, Number 5
Fate and Effects of Pollutants
tion of Groundwater:
An Evaluation of Environmental
Policy. 1. Am.
Water Resour. Assoc .. 34, 131 I.
Logue, K.; Corwin, D.L.; and Ellsworth, T.R. (1998) The Challenge of
Predicting Nonpoint Source Pollution. Environ. Sci. Techno!., 32,
BOA.
Lopes, T.J., and Bender, D.A. (1998) Nonpoint Sources of Volatile Organic Compounds
in Urban Areas-Relative
Importance
of Land
Surfaces and Air. Environ. Pol/ut., 101,221.
Lusby, F.E.; Gibbs, M.M.; Cooper, A.B.; and Thompson,
Fate of Groundwater
K. (1998) The
Ammonium in a Lake Edge Wetland. J. Environ.
Lu, X., and Higgitt, D.L. (1998) Recent Changes of Sediment Yield in the
and Amador, lA.
of Phosphorus
Retention
Environ. Qual., 27, 895.
Mahamah, D.S. (1998) Simplifying
(1998) Spatial and Temporal
in a Riparian
Assumptions
Forest Soil. J.
in Water Quality Mod-
eling. Eco!' Model.. 109, 295.
Manguerra, H.B., and Engel, B.A. (1998) Hydrologic Parameterization
of
Watersheds for Runoff Prediction Using SWAT. J. Am. Water Resour. Assoc .. 34, 1149.
Martins, J.M., and Mermoud, A. (1998) Sorption and Degradation of Four
Nitroaromatic Herbicides in Mono and Multi-Solute SaturatedlUnsaturated Soil Batch Systems. J. Contam. Hydrol., 33, 187.
Masse, L.; Patni, N.K.; Jui, P.Y.; and Clegg, B.S. (1998) Groundwater
Quality Under Conventional and No Tillage: II. Atrazine, Deethylatrazine, and Metolachlor. .I. Environ. Qua!., 27,877.
Massone, H.E.; Martinez, D.E.; Coinchi, J.L.; and Bocanegra, E. (1998)
Suburban Areas in Developing Countries and Their Relationship to
Groundwater Pollution: A Case Study of Mar del Plata, Argentina.
Environ. Manage., 22, 245.
Matin, M.A.; Malek, M.A.; Amin, M.R.; Rahman, S.; Khatoon, J.; Rahman, M.; Aminuddin, M.; and Mian, A.J. (1998) Organochlorine
Insecticide Residues in Surface and Underground Water from Different Regions of Bangladesh. Agric. Ecosyst. Environ., 69, 11.
Matlock, M.D.; Matlock, M.E.; Storm, D.E.; Smolen, M.D.; and Henley,
W.J. (1998) Limiting Nutrient Determination in Lotic Ecosystems
Using a Quantitative Nutrient Enrichment Periphytometer. .I. Am.
Water Resour. Assoc., 34, 1141.
McMahon, G., and Harned, D.A. (1998) Effect of Environmental Setting
on Sediment, Nitrogen, and Phosphorus Concentrations in AlbemarlePamlico Drainage Basin, North Carolina and Virginia, USA. Environ.
Manage., 22,887.
McMurry, S.W.; Coyne, M.S.; and Perfect, E. (1998) Fecal Coliform
Transport Through Intact Soil Blocks Amended with Poultry Manure.
.I. Environ. Qual., 27, 86.
Meals, D.W., and Budd, L.F. (1998) Lake Champlain Basin Nonpoint
Source Phosphorus Assessment. J. Am. Water Resour. Assoc., 34,
251.
.
Meredith, D.; Maidment, C.; and Gibbs, K. (1998) Total Ammonia Monitoring Using an Optrode and an Electrochemical Sample pH Adjusting System. Water Sci. Techno!. (G.B.), 37, 301.
Mickelson, S.K.; Baker, J.L.; Melvin, S.W.; Fawcett, R.S.; Tierney, D.P.;
and Peter, C.J. (1998) Effects of Soil Incorporation and Setbacks on
Herbicide Runoff from a Tile-Outlet Terraced Field. J. Soil Water
Conserv., 53, 18.
Mills, M.S., and Simmons, N.D. (1998) Assessing the Ground-Water
Contamination Potential of Agricultural Chemicals: A Flexible Approach to Mobility and Degradation Studies. Pestic. Sci., 54,418.
Moreau-Kervevan, C., and Mouvet, C. (1998) Adsorption and Desorption
of Atrazine, Deethylatrazine, and Hydroxyatrazine by Soil Components. J. Environ. Qual., 27, 46.
Napier, T.L., and Johnson, E.J. (1998) Impacts of Voluntary Conservation
Initiatives in the Darby Creek Watershed of Ohio . .I. Soil Water
Conserv., 53, 78.
Navulur, K.C.S., and Engel, B.A. (1998) Groundwater Vulnerability Assessment to Non-Point Source Nitrate Pollution on a Regional Scale
Using GIS. Trans. Am. Soc. Agric. Eng., 41, 1671.
Literature Review 1999
Using GIS and Multivariate
Statistical
Modelling
Methods.
of
Water
Sci. Technol. (G.B.), 38, 191.
Novak, J.M.; Watts, D.W.; Stone, K.C.; Johnson, M.H.; and Hunt, P.G.
(1998a) Pesticides and Metabolites
in the Shallow Groundwater
Eastern Coastal Plain Watershed.
Trans. Am. Soc. Agric. Eng., 41,
1383.
Novak, J.M., and Watts, D.W. (1998b) Pesticide Concentration
of an
Variations
Correlated with Well Bore Volume Removal in Shallow Coastal Plain
Ground Water. J. Environ. Sci. Health, B33, 609.
from Agriculture
and Phosphorus
Losses
into Surface Waters; The Effects of Policies and
Measures in The Netherlands. Water Sci. Techno/. (G.B.), 37, 19.
Upper Yangtze, China. Environ. Manage., 22,607.
Variability
T.; Pasztor, L.; and Szabo, J. (1998) Stochastic
N-Leaching
Oenema, 0., and Roest, C.W.J. (1998) Nitrogen
Qua!., 27,459.
Lyons, J.B.; Gorres, lH.;
Nemeth,
Ohrui, K., and Mitchell, M.J. (1998) Effects of Nitrogen Fertilization on
Stream Chemistry of Japanese Forested Watersheds. Water, Air, Soil
Pol/ut. (Neth.), 107,219.
Osuch-Pajdzinska.
E., and Zawilski, M. (l998a)
Model for Storm Sewer
Discharge. 11:Calibration and Verification . .I. Environ. Eng., 124,600.
Osuch-Pajdzinska,
E., and Zawilski, M. (1998b) Model of Storm Sewer
Discharge. I. Description. J. Environ. Eng., 124, 593.
Pang, X.P.; Gupta, S.c.; Moncrief, J.F.; Rosen, C.J.; and Cheng,
H.H.
(1998) Evaluation of Nitrate Leaching Potential in Minnesota Glacial
Outwash Soils Using the CERES-Maize Model. .I. Environ. Qual., 27,
75.
Parkhurst, D.F., and Stem, D.A. (1998) Determining Average Concentrations of Cryptosporidium and Other Pathogen in Water. Environ. Sci.
Techno!., 32, 3424.
Parry, R. (1998) Agricultural Phosphorus and Water Quality: A U.S.
Environmental Protection Agency Perspective. J. Environ. Qual., 27,
258.
Parson, S.C.; Hamlett, J.M.; Robillard, P.D.; and Foster, M.A. (1998)
Determining the Decision-Making
Risk from AGNPS Simulations.
Trans. Am. Soc. Agric. Eng., 41, 1679.
Patni, N.K.; Masse, L.; and Jui, P.Y. (1998) Groundwater Quality Under
Conventional and No Tillage: I. Nitrate, Electrical Conductivity, and
pH. J. Environ. Qual., 27, 869.
Pelley, J. (1998) The Challenge of Watershed Cleanup. Water Environ.
Techno!., 32, 364A.
Perniel, M.; Ruan, R.; and Martinez, B. (1998) Nutrient Removal from a
Stormwater Detention Pond Using Duckweed. Appl. Eng. Agric., 14,
605.
Perrin, T.S.; Boettinger, J.L.; Drost, D.T.; and Norton, J.M. (1998) Decreasing Nitrogen Leaching from Sandy Soil with AmmoniumLoaded Clinoptilolite. J. Environ. Qual., 27, 656.
Pettersson, T.J.R. (1998) Water Quality Improvement in a Small Stormwater Detention Pond. Water Sci. Techno/. (G.B.), 38, 115 .
Pisano, W.C. (1998) Pollutant Control for Stormwater Events. Water
Environ. Technol., 10,41.
Prato, T., and Kang, C. (1998) Economic and Water Quality Effects of
Variable and Uniform Application of Nitrogen. J. Am. Water Resour.
Assoc., 34, 1465.
Przepiora, A.; Hesterberg, D.; Parsons, J.E.; Gilliam, J.W.; Cassel, D.K.;
and Faircloth, W. (1998) Field Evaluation of Calcium Sulfate as a
F10cculant for Sedimentation Basins. J. Environ. Qual., 27,669.
Qiu, Z., and Prato, T. (1998) Economic Evaluation of Riparian Buffers in
an Agricultural Watershed . .I. Am. Water Resour. Assoc., 34, 877.
Rai, S.c., and Sharma, E. (1998) Hydrology and Nutrient Flux in an
Agrarian Watershed of the Sikkim Himalayas . .I. Soil Water Conserv.,
53, 125.
Ramanarayanan, T.S.; Storm, D.E.; and Smolen, M.D. (1998) Analysis of
Nitrogen Management Strategies Using EPIC. J. Am. Water Resour.
Assoc., 34, 1199.
Rice, C.E., and Kadavy, K.C. (1998) Low-Drop Grade-Control Structure.
Trans. Am. Soc. Agric. Eng., 41, 1337.
Rice, R.W., and Izuno, F.T. (1998) Techniques for Assessing BMP Effectiveness in the Absence of Historical Baseline Data. Appl. Eng. Agric.,
14,381.
Ritter, W.F.; Scarborough, R.W.; and Chirnside, A.E.M. (1998) Winter
1067
Fate and Effects of Pollutants
Cover Crops as a Best Management
Practice for Reducing Nitrogen
Leaching. J. COn/am. Hydrol., 34, I.
Robinson,
J.B.; Hazell,
the 8th National
W.F.; and Garrett,
Streamflow, and Water-Quality
R.G. (1998)
Precipitation,
Data from Selected Sites in the City of
Charlotte and Mecklenburg County, North Carolina,
File Report 98-67, U.S. Geo\. Survey, Reston, Va.
1995-97. Open
'
Robinson, K.M., and Cook, K.R. (1998) Stress Measurement Upstream of
an Overfall. Trans. Am. Soc. Agric. Eng., 41, 1019.
Robins, N.S. (1998) The Quality of Shallow Groundwaters in Northern
Ireland. J. Chartered Inst. Water Environ. Manage., 12, 163.
Roger, S.; Montrejaud-Vignol,
M.; Andral, M.C.; Herremans, L.; and
Fortune, J.P. (1998) Mineral, Physical and Chemical Analysis of the
Solid Matter Carried by Motorway Runoff Water. Water Res. (G.B.),
32, 1119.
Rothrock, J.A.; Barten,
Aquatic
P.K.; and Ingman,
Biointegrity
in the Blackfoot
G.L. (1998) Land Use and
River Watershed,
Montana.
J. Am. Water Resour. Assoc., 34, 565.
Rudek, J.; Taylor, M.E.; Wilcove, D.S.; Preyer, J.B.; Duval, M.A.; Bonnie,
R.; and Riva, X. (1998)
Soiled Streams:
Cleaning
Up Sediment
Pollution in North Carolina Waters. Environ. Defense Fund, 12,355.
Rudolph,
D.L.; Barry, D.A.J.; and Goss, M.J. (1998) Contamination
in
Ontario Farmstead Domestic Wells and Its Association with Agriculture: 2. Results from Multilevel Monitoring Well Installations. J.
Contam. Hydro/., 32, 295.
Ryals, S.C.; Genter, M.B.; and Leidy, R.B. (1998) Assessment
of Surface
Water Quality on Three Eastern North Carolina Golf Courses. Environ. Toxicol. Chem., 17, 1934.
Sans alone, 1.1.; Koran, J.M.; Smithson, J.A.; and Buchberger,
Physical Characteristics
Sievers, D.M. (Ed.) (1998) On-Site Wastewater Treatment: Proceedings of
S.G. (1998)
of Urban Roadway Solids Transported
Dur-
ing Rain Events. J. Environ. Eng .. 124,427.
Symposium
on Individual
and Small Community
Sewage Systems. ASAE Publication 03-98, Am. Soc. Agric. Eng., St.
Joseph, Mich.
Sims, J.T.; Simard, R.R.; and Joern, B.C. (1998) Phosphorus
Loss in
Agricultural Drainage: Historical Perspective and Current Research.
J. Environ. Qual., 27,277.
Snyder, N.J.; Mostaghimi, S.; Berry, D.F.; Reneau, R.B.; Hong, S.; McClellan, P.W.; and Smith, E.P. (1998) Impact of Riparian Forest
Buffers on Agricultural Nonpoint Source Pollution. J. Am. Water
Resour. Assoc., 34, 385.
Sojka, R.E.; Lentz, R.D.; Ross, e.W.; Trout, T.J.; Bjorneberg, D.L.; and
Aase, J.K. (1998) Polyacrylamide Effects on Infiltration in Irrigated
Agriculture. J. Soil Water Conserv., 53, 325.
Sojka, R.E.; Lentz, R.D.; and Westermann, D.T. (1998) Water and Erosion
Management
with Multiple Applications
of Polyacrylamide.
Soc. Am. J., 62, 1672.
Springer, A.E., and Bair, E.S. (1998) Natural-Gradient
Transport of Bro-
mide, Atrazine, and Alachlor in an Organic Carbon-Rich
Environ. Qual., 27, 1200.
Spruill, T.B.; Hamed, D.A.; Ruhl, P.M.; Eimers,
Soil Sci.
Aquifer. J.
J.L.; McMahon,
G.;
Smith, K.E.; Galeone, D.R.; and Woodside, M.D. (1998) Water Quality in the Albemarle-Pamlico
Drainage Basin, North Carolina, 1992-
95. USGS Circular 1157. U.S. Geo!. Survey, Denver, Colo.
Srivastava, P.; Costello, T.A.; Edwards, D.R.; and Ferguson, J.A. (1998)
Validating a Vegetative Filter Strip Performance
Soc. Agric. Eng., 41, 89.
Stamm, e.; Huhler, H.; Gachter, R.; Leuenberger,
(1998) Preferential
Transport
of Phosphorus
Model. Trans. Am.
J.;and
Wunderli,
H.
in Drained Grassland
Soils. 1. Environ. Qual.. 27,515.
Saporito, L.S., and Lanyon, LE. (1998) Evaluating Management and Soil
and Weather Contributions to Potential Nitrate Leaching from a
Stange, C.F.; Diekkruger, B.; and Nordmeyer, H. (1998) Measurement and
Simulation of Herbicide Transport in Macroporous Soils. Pestic. Sci.,
Pennsylvania Dairy Farm Using NLEAP. J. Environ. Qual., 27, 1367.
Schreiber, J.D., and Cullum, R.F. (1998) Tillage Effects on Surface and
52,241..
Steinheimer, T.R.; Scoggin, K.D.; and Kramer, L.A. (l998a)
Groundwater Quality in Loessial Upland Soybean Watersheds.
Am. Soc. Agric. Eng .. 41, 607.
Trans.
Agricultural
Chemical Movement Through a Field-Size Watershed in Iowa: Surface Hydrology and Nitrate Losses in Discharge. Environ. Sci. Tech-
Scott, e.A.; Geohring, L.D.; and Walter, M.F. (1998a) Water Quality
Impacts of Tile Drains in Shallow, Sloping, Structured Soils as
nol., 32, 1048.
Steinheimer, T.R.; Scoggin, K.D.; and Kramer, L.A. (1998b) Agricultural
Affected by Manure Application. App/. Eng. Agric., 14, 599.
Scott, C.A.; Walter, M.F.; Brooks, E.S.; Boll, J.; Hes, M.B.; and Merrill,
M.D. (l998b) Impacts of Historical Changes in Land Use and Dairy
Herds on Water Quality in the Catskills Mountains. J. Environ. Qual.,
27,1410.
Shapir, N.; Mandelbaum, R.T.; and Jacobsen, C.S. (1998) Rapid Atrazine
Mineralization Under Denitrifying Conditions by sp., Strain ADP in
Aquifer Sediments. Environ. Sci. Technol., 32, 3789.
Shaw, L.J., and Bums, R.G. (I 998a) Biodegradation-Transport
Interactions
Chemical Movement Through a Field-Size Watershed in Iowa: Subsurface Hydrology and Distribution of Nitrate in Groundwater. Environ. Sci. Technol., 32, 1039.
Stoddard, C.S.; Coyne, M.S.; and Grove, J.H. (1998) Fecal Bacteria Survival and Infiltration Through a Shallow Agricultural Soil: Timing
and Tillage Effects. J. Environ. Qual., 27, 1516.
Stone, K.e.; Hunt, P.G.; Johnson, M.H.; and Matheny, T.A. (1998a)
Nitrate-N Distribution and Trends in Shallow Groundwater on an
Eastern Coastal Plain Watershed. Trans. Am. Soc. Agric. Eng., 41,59.
Stone, K.C.; Hunt, P.G.; Humenik, F.J.; and Johnson, M.H. (l998b) Impact
of Swine Waste Application on Ground and Stream Water Quality in
of Pulse Applied 2,4-D in Repacked
Environ. Qual., 27, 1472.
Soil Column Microcosms.
J.
Shaw, L.J., and Bums, R.G. (l998b) Biodegradation of 2,4-D in Noncontaminated Grassland Soil Profile. J. Environ. Qual.. 27, 1464.
Shirmohammadi, A.; Ulen, B.; Bergstrom, L.F.; and Knisel, W.G. (1998)
Simulation of Nitrogen and Phosphorus Leaching in a Structured Soil
Using GLEAMS and a New Submodel, "PARTLE." Trans. Am. Soc.
Agric. Eng., 41, 353.
Shukla, S.; Mostaghimi, S.; Shanholtz, V.O.; and Collins, M.e. (1998) A
GIS-Based Modeling Approach for Evaluating Groundwater Vulnerability to Pesticides. J. Am. Water Resour. Assoc., 34, 1275.
Siegrist, S.; Schaub, D.; Pfiffner, L.; and Mader, P. (1998) Does Organic
Agriculture Reduce Soil Erodibility? The Results of a Long-Term
Field Study on Loess in Switzerland. Agric. Ecosyst. Environ., 69,
252.
Sieker, F. (1998) On-Site Stormwater Management as an Alternative to
Conventional Sewer Systems: A New Concept Spreading in Germany.
Water Sci. Technol. (G.B.), 38, 65.
Sieker, H., and Klein, M. (1998) Best Management Practices for Stormwater-Runoff with Alternative Methods in a Large Urban Catchment
in Berlin, Germany. Water Sci. Technol. (G.B.), 38, 91.
1068
an Eastern Coastal Plain Watershed. Trans. Am. Soc. Agric. Eng., 41,
1665.
Stone, K.e.; Hunt, P.G.; Johnson, M.H.; and Coffey, S.W. (l998c)
GLEAMS Simulation of Groundwater Nitrate-N from Row Crop and
Swine Wastewater Spray Fields in the Eastern Coastal Plain. Trans.
Am. Soc. Agric. Eng., 41,51.
Stout, W.L.; Gburek, W.J.; Schnabel, R.R.; Folmar, G.J.; and Weaver, S.R.
(1998) Soil-Climate Effects on Nitrate Leaching from Cattle Excreta.
J. Environ. Qual., 27, 992.
Strecker, E.W. (1998) Considerations and Approaches for Monitoring the
Effectiveness of Urban BMPs. Nat!. Conf. Retrofit Opportunities
Water Resour. Protect.
Sun, G.; Riekerk, H.; and Comerford, N.B. (l998a) Modeling the Hydrologic Impacts of Forest Harvesting on Horida Flatwoods. J. Am.
Water Resour. Assoc., 34, 843.
Sun, G.; Riekerk, H.; and Comerford, N.B. (l998b) Modeling the Forest
Hydrology of Wetland-Upland Ecosystems in Florida. J. Am. Water
Resour. Assoc., 34, 827.
Suzuki, T.; Kondo, H.; Yaguchi, K.; Maki, T.; and Suga, T. (1998)
Water Environment
Research,
Volume 71, Number 5
Fate and Effects of Pollutants
Estimation of Leachability and Persistence of Pesticides at Golf
Courses from Point-Source Monitoring and Model To Predict Pesticide Leaching to Groundwater. Environ. Sci. Technol., 32, 920.
Tan, C.S.; Drury, e.F.; Soultani, M.; van Wesenbeeck, I.J.; Ng, H.Y.F.;
Gaynor, J.D.; and Welacky, T.W. (1998) Effect of Controlled Drain-
Wall, G.R.; Phillips, PJ.; and Riva-Murray,
age and Tillage on Soil Structure and Tile Drainage Nitrate Loss at the
Field Scale. Water Sci. Technol. (G.B.), 38, 103.
Templeton, S.R.; Zilberman, D.; and Yoo, SJ. (1998) An Economic
Perspective on Outdoor Residential Pesticide Use. Environ. Sci. Tech-
430.
Weed, D.AJ.;
nol., 32,416A.
Thas, 0.; Van Vooren,
1.; and Ouoy, J.P. (1998) Nonparametric
Test
Performance for Trends in Water Quality with Sampling Design
Applications. J. Am. Water Resour. Assoc., 34, 347.
Thomsen,I.K., and Christensen, B.T. (1998) Cropping System and Residue
Management
Effects on Nitrate Leaching
£Cosyst. Environ., 68, 73.
Thorolfsson, S.T. (1998) A New Direction
Pollution
Management
and Crop Yields. Agric.
in the Urban Runoff
and
Water Sci.
Technol. (G.B.), 38, 123.
Thorsen, M.; Jorgensen, P.R.; Felding, G.; Jacobsen, O.H.; Spliid, N.H.;
and Refsgaard, lC. (1998) Evaluation of a Stepwise Procedure for
Comparative Validation of Pesticide Leaching Models. J. Environ.
Qual., 27, 1183.
Tiktak, A.; ven der Linden, A.M.; and van der Pas, 1.J.T. (1998) Application of the Pesticide Transport Assessment Model to a Field Study
in a Humic Sandy Soil in Vredepeel, The Netherlands. Pestic. Sci., 52,
321.
Toth, J.D., and Fox, R.H. (1998) Nitrate Losses from a Com-Alfalfa
Rotation: Lysimeter Measurement of Nitrate Leaching. J. Environ.
Qual., 27, 1027.
Trabada-Crende, F., and Vinten, AJ.A. (1998) Assessing the Effects of
Land Management and Catchment Hydrology on Well Water Quality
in a Designated Nitrate Vulnerable Zone. Agric. Syst., 57, 523.
Truman, C.e.; Leonard, R.A.; and Johnson, A.W. (1998) Fenamiphos
Transport, Transformation, and Degradation in a Highly Weathered
Soil. Trans. Am. Soc. Agric. Eng., 41, 663.
Tufford, D.L.; McKellar, H.N.; and Hussey, J.R. (1998) In-Stream Nonpoint Source Nutrient Prediction with Land-Use Proximity and Seasonality. J. Environ. Qual., 27, 100.
Ulen, B.; Shirmohammadi,
A.; and Bergstrom, 1.F. (1998) Phosphorus
Transport Through a Clay Soil. J. Environ. Sci. Health, A33, 67.
Uri, N.D. (1998) The Developmental Consequences of the Conservation
Tillage Adoption Decision in Agriculture in the United States. Water,
Air, Soil Pol/ut. (Neth.), 105, 9.
U.S. Environment Protection Agency (1998) Report of the Federal Advisory Committee on the Total Maximum Daily Load Program. EPA1001R-98, U.S. EPA, Office of the Administrator, Washington, D.C.
Van Klaveren, R.W., and McCool, D.K. (1998) Erodibility and Critical
Shear of a Previously Frozen Soil. Trans. Am. Soc. Agric. Eng., 41,
1315.
Van Liew, M.W. (1998) Prediction of Sediment Yield on a Large Watershed in North Central China. Trans. Am. Soc. Agric. Eng., 41, 599.
Verchot, L.V.; Franklin, E.e.; and Gilliam, J.W. (1998) Effects of Agricultural Runoff Dispersion on Nitrate Reduction in Forested Filter
Zone Soils. Soil Sci. Soc. Am. J., 62, 1719.
Vervoort, R.W.; Radcliffe, D.E.; Cabrera, M.L.; and M. Latimore, M., Jr.
(1998) Field-Scale Nitrogen and Phosphorus Losses from Hayfields
Receiving Fresh Composted Broiler Litter. J. Environ. Qual., 27, 1246.
Viklander, M. (1998) Particle Size Distribution and Metal Content in Street
Sediments. J. Environ. Eng., 124, 761.
Wade, H.F.; York, A.e.; Morey, A.E.; Padmore, J.M.; and Rudo, K.M.
(1998) The Impact of Pesticide Use on Groundwater in North Carolina. J. Environ. Qual., 27, 1018.
Literature
Review
1999
in Canajoharie
Creek,
New York. J. Environ. Qual., 27,381.
Wan, Y., and EI-Swaify, S.A. (1998) Characterizing
by Partitioning
Interrill Sediment Size
Splash and Wash Processes. Soil Sci. Soc. Am. J., 62,
Kanwar, R.S.; Cambardella,
e.; and Moorman, T.B. (1998)
Alachlor Dissipation in Shallow Cropland Soil. J. Environ. Qual., 27,
767.
Wernick, B.G.; Cook, K.E.; and Schreier, H. (1998) Land Use and Streamwater Nitrate-N Dynamics in an Urban-Rural Watershed. J. Am.
Water Resour. Assoc., 34, 639.
White, S.K.; Cook, H.F.; and Garraway, 1.1. (1998) The Use of FertilizerFree Grass Buffer Strips To Attenuate
Nitrate Input to Marshland
Dykes. J. Chartered Inst. Water Environ. Manage.,
Whittemore,
in the City of Bergen, Norway.
K. (1998) Seasonal and Spatial
Patterns of Nitrate and Silica Concentrations
12, 54.
R.e. (1998) The BASINS Model. Water Environ. Technol.,
10,57.
Wichert, G.A., and Rapport, DJ. (1998) Fish Community
Measure of Degradation
Agricultural
and Rehabilitation
Structure as a
of Riparian Systems in an
Drainage Basin. Environ. Manage., 22, 425.
Williams, A.E.; Johnson, J.A.; Lund. L.1.; and Kabala, Z.1. (1998) Spatial
and Temporal Variations in Nitrate Contamination
California. J. Environ. Qual., 27, 1147.
of a Rural Aquifer,
Williams, R.I. (1998a) Modeling Pesticide Run-Off to Surface Waters. Part
II. Model Application. Pestic. Sci., 54, 121.
Williams, R.I. (1998b) Modeling Pesticide Run-Off to Surface Waters.
Part I: Model Theory and Development. Pestic. Sci., 54, ] 13.
Williamson, J.e.; Taylor, M.D.; Torrens, R.S.; and Vojvodic-Vukovic, M.
(1998) Reducing Nitrogen Leaching from Dairy Farm Effluent-Irrigated Pasture Using Dicyandiamide: A Lysimeter Study. Agric. £Cosyst. Environ., 69, 81.
Wong, J.W.C.; Chan, C.W.Y.; and Cheung, K.C. (1998) Nitrogen and
Phosphorus
eter Study.
Wu, 1.S.; Allan,
ization and
Leaching from Fertilizer Applied on Golf Course: LysimWater, Air, Soil Pollut. (Neth.), 107, 335.
CJ.; Saunders, W.1.; and Evett, J.B. (1998) CharacterPollutant Loading Estimation for Highway Runoff. J.
Environ. Eng., 124, 584.
Xing, B., and Pignatello, J.J. (1998) Competitive Sorption Between 1,3Dichlorobenzene or 2,4-Dichlorophenol
and Natural Aromatic Acids
in Soil Organic Matter. Environ. Sci. Technol., 32,614.
Xue, Y.; David, M.B.; Gentry, L.E.; and Kovacic, D.A. (1998) Kinetics
and Modeling of Dissolved Phosphorus Export from a Tile-Drained
Agricultural Watershed. J. Environ. Qual., 27,9]7.
Yan, W.; Yin, e.; and Tang, H. (1998) Nutrient Retention by Multipond
Systems: Mechanisms for the Control of N Source Pollution. J.
Environ. Qual., 27, 1009.
Younos, T.M.; Mendez, A.; Collins, E.R.; and Ross, B.B. (1998) Effects of
a Dairy Loafing Lot-Butter Strip on Stream Water Quality. J. Am.
Water Resour. Assoc., 34, 1061.
Yu, Z., and Schwartz,
Scale Hydrologic
F.W. (1998) Application of an Integrated BasinModel To Simulate Surface-Water and Ground-
Water Interactions. J. Am. Water Resour. Assoc., 34, 409.
Zebarth, B.1.; Hii, B.; Liebscher, H.; Chipperfield, K.; Paul, J.W.; Grove,
G.; and Szeto, S.Y. (1998) Agricultural Land Use Practices and
Nitrate Contamination in the Abbotsford Aquifer, British Columbia,
Canada. Agric. Ecosyst. Environ., 69, 99.
Zhang, X.C.; Nearing, M.A.; Miller, W.P.; Norton, 1.D.; and West, 1.T.
(l998a) Mode]ing Interrill Sediment Delivery. Soil Sci. Soc. Am. J.,
62,438.
Zhang, X.e.; Miller, W.P.; Nearing, M.A.; and Norton, 1.D. (l998b)
Effects of Surface Treatment on Surface Sealing, Runoff, and Interrill
Erosion. Trans. Am. Soc. Agric. Eng., 41, 989.
1069