United States
Environmental Protection
Agency
Municipal Environmental
Research Laboratory
Cincinnati OH 45268
Research and Development
EPA-600/S2-84-092 Sept. 1984
v>ERA Project Summary
Production and Management of
Leachate from Municipal
Landfills: Summary and
Assessment
James C.S. Lu, Bert Eichenberger, Robert J. Stearns, and Ihor Melnyk
Production and management of
leachate from municipal landfills were
evaluated to identify practical informa-
tion and useful techniques for design
engineers and site operators. Advan-
tages, limitations, and comparative
costs were also assessed for various
approaches to the problem. The study
addressed public health impacts, man-
agement options, and additional research
needs on the generation, control, and
monitoring of landfill eration, contol, and
monitoring of landfill leachates. Nu-
merous mathematical models have
been proposed for estimating leachate
generation, and they are usually based
on the water balance method. Several
fairly successful models are proposed
here for simulating the change in
leachate strength with increasing
landfill age of cumulative leachate
volume. A program to monitor the zone
of saturation is established to give a
prompt indication of groundwater
contamination.
This Project Summary was developed
by EPA's Municipal Environmental
Research Laboratory. Cincinnati, OH, to
announce key findings of the research
project that is fully documented in a
separate report of the same title (see
Project Report ordering information at
back).
Introduction
In 1990, a projected 295 to 341 million
metric tons of municipal refuse will be
produced in the United States. When
water passes through this refuse in a
sanitary landfill, it accumulates various
contaminants. This percolate or leachate
may then enter underlying groundwaters
and seriously degrade the water quality
of the aquifer. Landfill leachate may thus
exert a major environmental impact.
Leachate production can be minimized
or nearly eliminated by preventing water
contact with the refuse by the use of
surface and subsurface drainage and
properly selected cover material that is
graded and seeded with a high evapotran-
spiration (ET) crop. Various studies
concerning sanitary landfill behavior
have been conducted to understand,
delineate, and define significant manage-
ment options.
The objectives of this study were: (1) to
clarify the understanding of leachate
production and management options
through a critical review and analysis of
existing information; (2) to identify
practical information and techniques that
can be used by design engineers and site
operators; (3) to delineate weaknesses in
the available data base; and (4) to identify
useful techniques for estimating and
mitigating the environmental and public
health impacts of leachate generation.
The specific objectives were to document:
(1) current methods, advantages, and
limitations of various approaches; (2)
comparative costs; (3) additional research
needs on the generation, significances,
and associated costs of controlling and
monitoring leachate from municipal
landfills. Presentation of the results is in
terms of leachate generation, composition,
and migration, available control technol-
ogy, and environmental monitoring.
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Leachate Generation
Leachate generation at a landfill site
depends on many factors. Volume is
generally determined by the availability of
water, landfill surface conditions, refuse
conditions, and underlying soil conditions.
Factors affecting availability of water
include direct precipitation, surface run-
on, groundwater intrusion, irrigation,
refuse decomposition, and co-disposal of
liquid waste or sludge with refuse. In
most cases, precipitation (including
rainfall and snowfall) will be the principal
source of leachate. Many methods for
estimating leachate generation neglect
the effects of rainfall intensity, frequency,
or duration. Intensity influences the
impact of raindrops on the surface soil
particles, which could change infiltration
rates and leachate quantity. Frequency
and duration also affect infiltration and
runoff. Quantitative information on the
effects of such rainfall characteristics on
leachate generation is lacking. Snowmelt
usually occurs at rates considerably
below the infiltration capacity of unpacked
soils. Surface runoff from snowmelt may
therefore be rare.
Surface run-on is mostly affected by
surface topography and can be determined
by surface measurement, empirical
formulas, or graphic methods. The
rational method is expressed in terms of
uniform rate of rainfall intensity, landfill
area, and a runoff coefficient. The key to
successful estimation of surface runoff
by the rational method is the correct
choice of the coefficient dependent on
surface characteristics, type and extent
of vegetation, and surface slope. Cook's
method uses an empirical relationship
between drainage area and peak flow,
with modifications for climate, relief,
infiltration, vegetal cover, and surface
storage. Other methods include the
Burkli-Ziegler and McMath formulas.
Groundwater intrusion occurs if the
base of the landfill is below the ground-
water table. This condition may be
determined by a hydrologic investigation
and calculations using Darcy's Law.
Precise measurement of underground
flow is not feasible. The extent of
microbial activity and consequent water
production depends mainly on the amount
and pH of interstitial moisture, tempera-
ture, presence of oxygen, composition
and particle size of the refuse, organisms
present, and the degree of mixing.
Decomposition is much faster under
aerobic than anaerobic conditions. Under
aerobic conditions, decomposition may
reduce volatile matter and carbon con-
centrations by 50% in a year.
The volume of water available for
leaching from disposal of sewage sludge
with municipal solid waste may be
affected by the type and amount of
sludge, moisture content, moisture-
holding capacity, and the effect of
compaction and decomposition of the
release of water. ET, which is the sum of
water loss by evaporation and transpira-
tion, is affected by vegetation and cover
material (type, dimension, compaction,
etc.), surface topography, temperature,
humidity, and wind speed above the
landfill. ET determination methods fall
into three general categories—theoretical,
analytical, and empirical. Various mea-
surement methods are soil-moisture
sampling, lysimeter measurements, and
adjusted pan evaporation. Many empirical
or theoretical equations have been
derived for estimating ET rates. Some
typical equations are the Hedke, Lowry-
Johnson, Blaney-Morin, Blaney-Criddle,
Thornwaite, and Penman equations.
Leachate may be channeled through the
refuse and dispersed by intermediate
cover layers, or it may seep through the
pores of the refuse. If no channeling has
occurred in the refuse, leachate will first
appear when soil cover and refuse reach
field capacity. The time required for the
first appearance of leachate can be
obtained using the moisture-routing
calculation or by using a graphic technique.
If channeling does occur, leachate will
not be produced until at least a portion of
the refuse reaches field capacity. Specific
information describing the effects of
management or operating practices on
leachate production is not available.
Numerous mathematical methods
have been used for quantitative estimates
of the volume of leachate generated from
landfills. The approaches are all derived
from the water balance principle—a one-
dimensional flow model based upon the
retention and transmission characteristics
of the refuse and cover soil. Although the
water balance method has been widely
used for estimating landfill leachate, the
accuracy and sensitivity of the method for
the actual landfill are less studied. More
than a hundred different approaches are
available for water balance calculations,
but no comparisons have been made to
identify which approach can achieve
better results, or which is suitable for
what types of landfill conditions. The
applicability and accuracy of the water
balance calculations can be determined
by analyzing the suitability of the approaches
and the closeness of the calculated
results to actual measurements. Site
verification of various leachate estima-
tion techniques is largely lacking, however.
Applicability and accuracy are difficult to
verify for actual landfills because of the
lack of accurate leachate generation data.
Selection of applicable leachate volume
estimation methods should thus be based
on the specific site circumstances,
availability of data, scientific and engin-
eering judgments, and the experience of
the designer and operator in leachate
generation estimation.
Numerous methods have been proposed
for determining infiltration capacity and
rate. Theoretical methods are not recom-
mended because of their highly simplified
nature and their requirement for deter-
mining special watershed properties.
Three general appoaches are: actual
measurement, estimation from runoff,
and empirical calculation. The American
Society of Civil Engineers (ASCE) empiri-
cal method is based on relative minimum
infiltration capacities and takes into
account vegetal covers. Equations also
exist for snowmelt infiltration.
Leachate Composition
Leachates are usually highly contam-
inated and can degrade surface water
and groundwater. Viruses are only
occasionally detected in leachates,
though their potential presence in
leachates of fresh refuse cannot be
overlooked. Bacterial and viral populations
decrease significantly with refuse age or
time of leaching. Elevated landfill temper-
atures resulting from biodegradation can
help to inactivate bacteria and destroy
viruses. The chemical characteristics of
leachate also contribute to bacterial
inactivation. Little work has been done
regarding fungi and parasites in leachate.
The rate of solubilization of a refuse
mass is governed by specific microbial
populations dependent on chemical and
physical processes, including pH effects,
redox effects, precipitation, ion exchange,
adsorption and complexation, biological
effects, physical sorption effects, and
temperature. These processes create a
highly complex and dynamic system and
considerable variability in leachate
composition.
Leachate composition is a function of
numerous factors, including those inher-
ent in the refuse mass and landfill
location, and those created by designers
and site operators. The chemical and
microbiological character of refuse is
largely uncontrollable. Ambient tempera-
tures and rainfall are unalterable charac-
teristics, but refuse density, permeability,
depth, and water application can be
regulated. Compared with unshredded
refuse, shredded material yields increased
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landfill field capacity, a greater concen-
tration of pollutants in leachate, and a
higher rate of pollutant removal per
volume of leachate. Conversely, baling
produces a more dilute leachate, delays
attainment of landfill field capacity, and
removes less mass per volume of leachate
than shredded or unbaled refuse. Higher
rates of water application produce more
dilute leachate and greater mass removals
as a function of time. Increasing landfill
depth promotes stronger leachate. Land-
fill temperature fluctuates with the
seasonal ambient temperature variation
near the landfill surface, but these
amplitudes are less pronounced with
increased landfill depth.
The addition of municipal wastewater
treatment plant (WWTP) sludges or
industrial sludges to municipal landfills
provides both beneficial and adverse
effects on leachates. WWTP sludge and
refuse admixtures accelerate the rate of
stabilization of biodegradable organic
matter. The addition of industrial waste
may cause more toxic elements to occur
in leachates and may adversely affect the
biochemical stabilization processes.
Some of the specific findings are as
follows:
1. Seeding municipal refuse with
primary sewage sludge increases
the biological stabilization rates of
organic pollutants.
2. Addition of septic tank pumpings
accelerates the methanogenic pro-
cess.
3. Bacterial loading does not increase.
4. Leachate organics and total dissolved
solids (TOS) are reduced.
5. Inorganic ion concentrations are
largely unaffected.
6. Admixed WWTP sludge and refuse
produces an acidic leachate with a
higher BOD, but chemical composi-
tion does not differ.
7. Co-disposal accelerates leachate
formation through the additional
moisture.
8. Epidemiological evidence of diseases
resulting from WWTP sludge co-
disposal is lacking.
The leaching trends of chemically
stabilized and unstabilized industrial
wastes disposed with municipal solid
waste (MSW) are as follows:
1. The release of major metal contami-
nants from treated or untreated
electroplating sludge was not ob-
served when it was disposed with
MSW.
2. Untreated chlorine production brine
sludge disposed with MSW releases
significant quantities of aluminum.
cadmium, copper, chJorine, mercury,
sodium, and other dissolved solids.
3. Disposal of MSW with chemically
stabilized chlorine production brine
sludge significantly reduces the
mass release of toxic metals.
4. Disposal of MSW with calcium
fluoride and sewage sludge improves
leachate quality with respect to
BOD, COD, TOC, alkalinity, pH, and
iron.
Two approaches can be used to model
the composition of leachates as a
function of time or cumulative leachate
volume: (1) to describe quantitatively the
physical, chemical, and biological pro-
cesses that occur during leaching, and (2)
to avoid mathematical expression and
focus on leachate concentration histories.
The models are sensitive to such factors
as refuse placement and composition,
hydraulic phenomena, and landfill con-
figuration. Agreement of the various
models with experimental data ranges
from fair to very good. At present,
leachate composition models are appro-
priate primarily for research purposes,
since as mathematical expressions they
merely interpret experimental results.
Leachate Migration
Soils are chemically sorbent bodies
consisting of: (1) inert chemical compounds,
(2) difficult and easily soluble substances,
(3) soluble salts and acids, (4) complex
insoluble compounds, and (5) a wide
variety of organisms. Soil represents a
medium in which a series of complex
biological activities are occurring simul-
taneously. Soil properties most useful in
predicting the mobility of leachate
contaminants are: (1) texture, (2) content
of hydrous oxides, (3) type of content of
organic matter, (4) particle size distribu-
tion, (5) cation exchange capacity, and (6)
pH. The attenuation and migration of
contaminants in the soil and water
system are influenced by diffusion and
dispersion, dilution, straining, precipita-
tion/dissolution, adsorption/desorption,
complexation, ion exchange, redox, and
microbial activity.
The most important physical properties
relative to leachate migration are diffusion
and dispersion, dilution, sorption, and
straining. Hydrodynamic dispersion is the
result of variations in pore velocities
within a soil. It is effective in attenuating
the maximum constituent concentration
rather than the total quantity of the
constituent in a pulse or slug of leachate.
Complexation involves the reaction of
metal ions with inorganic anions and
organic liquids. Complex formation
affects attenuation and migration in two
ways: In solution, it greatly increases the
concentration of constituents by forming
soluble complexes; or, if the complex
formation exists between the soluble
constituents and solid surfaces, the
constituents levels decrease. Most ion
exchange effects orginate from exchange
sites on layered silicate clays and organic
matter. The exchange capacity of soils is
affected by the kind of quantity of clay
mineral and organic matter and the pH of
the soil/water solution. Redox reactions
occur when redox potential in leachates
is different from that of soil solutions.
Redox reactions are greatly affected by
degradation of organic compounds in the
soil. Through biological assimilation, the
trace metals may be transformed into
microbial tissue and immobilized. The
migration of trace metals in the soil/water
system is extremely complex. The fate of
chlorinated hydrocarbons, is very difficult
to predict. Volatilization, microbial de-
gradation, chemical hydrolysis, oxidation,
and sorption can be involved. The fate of
pesticides in soil/water systems involves
adsorption/desorption, microbial decom-
position, volatilization, soil moisture, and
physical properties of the soil. Adsorption
/desorption is considered most important.
Virus survival depends on soil moisture
content, temperature, pH, nutrient avail-
ability, and antagonisms. Viruses that
penetrate the soil surface are expected to
survive longer than those retained near
the surface.
Leachate migration models can be
classified into four generic categories:
descriptive, physical, analog, and mathe-
matical models. The models can also be
subcategorized by method of analysis and
particular approach. Empirical models
are based completely on observation
and/or experimentation. Conceptual
models use equations based on conser-
vation of mass, energy, and momentum.
In a deterministic model, all input
variables and system parameters are
assumed to have fixed mathematical
relationship with each other. Stochastic
models take into account intrinsic ran-
domness associated with parameters.
Static models evaluate steady-state
conditions, and dynamic models evaluate
changing variables. One-, two-, and
three-dimensional models may also be
used.
Available Control Technology
Environmental control technologies
are divided into four areas: Groundwater
control, leachate composition control,
collection systems, and treatment methods.
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Groundwater control measures are
presented in terms of groundwater/leach-
ate isolation and leachate plume control.
The groundwater/leachate isolation
methods can be defined as those approaches
by which contaminants are contained
within the fill and not permitted to
migrate into the groundwater. The
available control techniques include
synthetic liners, bottom sealers, slurry
trenches, grout curtains, and sheet piling
cutoff walls. The liners may be used both
as collection devices and as means for
isolating leachate. Bottom sealing offers
advantanges, especially in coarse soils
and gravels. The seal can prevent
groundwater from entering the fill and
impound the leachates formed. A slurry
trench prevents the horizontal subsurface
movement of water. Its advantages
include simple construction methods,
leachate-resistant bentonites, low main-
tenance, and minimal liner deterioration.
Slurry trenches are most effective where
a shallow groundwater condition exists
and an impermeable bedrock stratum is
available for contact with the barrier. A
grout curtain performs a function similar
to that of a slurry trench. Advantages of
sheet piling cutoff walls over slurry
trenches and grout curtains are ease of
construction, maintenence-free nature,
and low construction costs.
Plume control refers to efforts to isolate
a contaminated groundwater body.
Methods involve drains to intercept up-
gradient groundwater to lower the water
table, well point systems to prevent
groundwater flow through the fill or
leachate collection down gradient, and
deep-well systems that are a deeper form
of the well point systems. Surface water
control measures such as contour grading,
surface water diversion, surface sealing,
and revegetation are used to minimize
the quantity of water entering the landfill.
The purpose of leachate composition
control is to reduce the strength and
contaminant flux of leachate. Leachate
recirculation offers advantages such as
accelerated refuse stabilization, and
treatment systems are not always required.
Co-disposal of sewage sludge or alkaline
wastes can help to accelerate stabilization.
The use of limestone as an additional
attenuation layer is an effective, low-cost
aid in controlling the migration of heavy
metals.
The approaches to leachate treatment
are biological (aerobic and anaerobic)and
physical/chemical (precipitation, adsorp-
tion, coagulation, oxidation, and reverse
osmosis). Newly formed landfill leachate
is best treated by biological processes,
whereas leachate from stabilized landfills
is best treated with physical/chemical
methods. Aerobic treatment can effec-
tively remove organic matter and metals
from leachate. Removal of 90% to 99% of
BOD and COD and some metal removal
have commonly been reported. Problems
with aerobic treatment include long
treatment times, foaming, nutrient defi-
ciencies, toxic inhibition, and oxygen
depletion. Anaerobic treatment has been
effective in reducing organic loads:
Organic removals of 90% to 99% have
been demonstrated. Advantages over
aerobic treatment are low solids buildups
and an absence of aeration requirements,
which allows energy savings. Treatment
times are comparable. A major product of
anaerobic digestion is methane, which
can be used as an energy source.
The successful treatment of high-
strength leachates requires combinations
of biological and physical/chemical pro-
cesses. The design of a treatment system
depends not only a leachate character,
but on location. Landfills near a wastewa-
ter treatment plant may take advantage of
the facility, but distance sites will require
an aerated lagoon, land application, or a
complete treatment system. Treatment
costs may represent 25% or more of total
landfill costs.
Environmental Monitoring
The zone of aeration is that area
beneath the top soil and overlying the
water table in which pore space co-exists
with air, or in which the geologic
materials are unsaturated. Monitoring
the zone of aeration may be achieved with
or without sampling. Sampling approaches
include pore water extraction from soil
cores and deployment of pressure/vacuum
lysimetersto obtain in situ water samples.
The water samples may be analyzed for
major anions, trace metals, TOC, pH,
specific conductance, organics, and other
specific constituents. Core samples
provide information on physical charac-
teristics such as soil texture, water
content, hydraulic conductivity, and bulk
density. For shallow sampling of soils and
vadose waters, traditional hand augers
and bucket-type samplers may be used.
For deeper sampling, standard drilling
equipment is required.
Nonsampling approaches to monitoring
require tensiometers, psychrometers,
electrical resistance blocks, and neutron
moisture logging. Nonsampling methods
provide for the determination of water
content and movement in the vadose
zone. Tensiometers employ a mercury
manometer to measure soil-water pres-
sures during unsaturated flow conditions.
Psychrometers use a porous bulb with a
chamber to measure relative humidity in
the soil. Electrical resistance blocks
measure either soil-water content or
pressure. The neutron thermalization
method measures changes in the volu-
metric water content within a soil horizon
and delineates perched water zones and
estimates flow rates.
The zone of saturation is that portion of
the groundwater system in which avail-
able pore space is occupied by water.
Monitoring within the zone of aeration
has traditionally been accomplished with
single-screened wells. But the cluster
well and the air-lift sampler allow for
multiple sampling points throughout the
aquifer. Multi-sampling wells provide a
vertical distribution of contaminants and
greater flexibility, especially in three-
dimensional volume monitoring.
Selection of the optimum location for
sampling and nonsampling devices is
largely site-specific. In all cases, the
devices are situated below the landfill to
maintain contact with interstitial waters.
Monitoring frequency should be flexible,
allowing for modifications at each site.
Monitoring parameters are determined
largely by the purpose of the monitoring
program (Table 1). Many researchers
have developed lists of key indicator
parameters. Their selection should be
modified, as required, to meet site-
specific situations.
EPA and the American Public Health
Association (APHA) provide detailed
descriptions of appropriate containers for
various chemical species and sampling
techniques. Methods are intended to
retard biological activity, retard hydrolysis
of chemical compounds and complexes,
and reduce the volatility of constituents.
Preservation techniques are generally
limited to pH control, chemical addition,
refrigeration, and freezing.
Conclusions and
Recommendations
The quantity of leachate produced from
a municipal landfill may vary considerably
with management or operating practices,
depending on whether leachate is viewed
as a short- or long-term problem. Opera-
tional factors which affect leachate
quantity may include: cover material
handling, watering prior to compaction,
watering following compaction, daily
variation in cell construction, and variation
in waste composition (e.g., municipal
refuse alone or codisposal of municipal
refuse and sewage sludge or industrial
wastes; milled or unmilled refuse)
Numerous mathematical methods
have been proposed for a quantitative
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Table 1. Monitoring Parameters and Applicable Situations
Parameter
Applicable situation
Suitability of aquifer as a drinking water source
Chlorine, iron, manganese, phenols, sodium, and sulfate
Specific conductance, pH, total organic carbon, and
total organic halogen
Need exists to identify facilities that
may be severely degrading present
and future drinking water supplies.
Groundwater contamination must
be assessed after it is determined
that a facility is leaking.
A threshold assessment must be
made as to whether a facility is leak-
ing.
estimation of the volume of leachate
generated from landfills and are usually
based on a mass balance approach (i.e.,
water balance method). Components of'
these models are relatively easy to
obtain, but other model variables such as
the surface runoff coefficients, runoff
curve number, and evapotranspiration
from the landfill surface are more difficult
to develop. Limited field data exists for
verification for many of the leachate
generation models. Therefore, the appli-
cability, accuracy, and sensitivity of
leachate generation models, is largely
unknown. Additional research should be
conducted regarding such variables as
water contribution from refuse degrada-
tion, refuse permeability, evapotranspira-
tion, surface runoff coefficients, and
runoff curve numbers.
The composition of leachate produced
from a municipal landfill is highly
variable, depending on factors such as
refuse composition, refuse processing,
landfill age, the rate of infiltration, landfill
depth, and landfill temperature. The
quality of leachate can be controlled to a
large degree. Shredding and baling of
refuse, landfill depth, and the rate of
water application to the landfill surface
can influence the rate at which contami-
nants are released from refuse, and can
determine whether leachates have a
long- or short-term pollution potential.
Based on empirical data garnered from
a number of studies addressing landfill
and leaching behavior, several models
have been developed which describe
leachate quality as a function of time or
cumulative leachate generation. The
most promising of these models attempts
to simulate the physical/chemical and
biological processes which occur during
leaching. Presently, however, the leachate
composition models are useful only in in-
interpreting experimental results rather
than in finding application to field-
scale problems.
Leachate migration models are based
upon constituent mass transport and
water flow equations. Numerous models
are available for predicting chemical and
physical migration; biological models,
however, are generally lacking. While a
large number of conceptual-mathematical
models exist, none are universally
applicable for the simulation of all the
physical, chemical, and biological pro-
cesses that are operative in a typical
waste disposal system. The complexity of
these processes, which operate in a
simultaneous and interactive manner, is
probably such that the development of a
generic model would be impractical
because the resulting program would
undoubtedly become so large and complex
that the cost of operating it would be
exorbitant.
Leachate control technology is a
relatively well-developed methodology
for the management of landfill leachates.
Various groundwater and surface water
control approaches are available for the
control of leachate into or out of the fill.
Approaches in which dewatering or
counter pumping (injection) is practiced
appear to be effective control measures,
although the long-term energy costs for
pumping are restrictive. Accelerated
stabilization processes such as leachate
recycling and nutrient addition are
promising, but require additional study.
Extensive liner technology is available;
however, field verification studies have,
in general, been inconclusive regarding
anticipated liner lifetime.
Vadose zone monitoring has received
little attention in contrast to the advanced
technology for monitoring in the zone of
saturation. This discrepancy reflects, to a
large extent, the greater complexity of
flow in the vadose zone, compared to
saturated flow, and the related problem of
obtaining a representative sample for
analysis. Incorporation of vadose zone
devices can provide an early warning of
potential groundwater pollution. If reme-
dial measures are implemented prior to
the onset of extensive groundwater con-
tamination, the associated renovation
costs could be reduced significantly.
Additionally, an effective vadose zone
monitoring network could reduce, or
largely preclude, the requirements for
groundwater monitoring. The savings in
costs for construction of groundwater
wells could be significant, particularly in
western regions where water tables are
often hundreds of feet deep. Vadose zone
monitoring requires additional study to
better define both the dominant pheno-
mena occurring in this zone, as well as
optimum monitoring equipment.
The full report was submitted in
fulfillment of Contract No. 68-03-2861 by
Calscience Research, Inc., under the
sponsorship of the U.S. Environmental
Protection Agency.
*USGPO: 1984-759-102-10664
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James C. S. Lu, Bert Eichenberger. and Robert J. Stearns are with Calscience
Research, Inc., Huntington Beach, CA 92647; the EPA author. Ihor Melnyk, is
with Municipal Environmental Research Laboratory, Cincinnati, OH 45268.
Wendy J. Davis-Hoover is the EPA Project Officer (see below).
The complete report, entitled "Production and Management of Leachate from
Municipal Landfills: Summary and Assessment," (Order No. PB 84-187 913;
Cost: $34.00, subject to change) will be available only from:
National Technical Information Service
5285 Port Royal Road
Springfield. V'A 22161
Telephone: 703-487-4650
The EPA Project Officer can be contacted at:
Municipal Environmental Research Laboratory
U.S. Environmental Protection Agency
Cincinnati, OH 45268
United States
Environmental Protection
Agency
Center for Environmental Research
Information
Cincinnati OH 45268
Official Business
Penalty for Private Use $300
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