EPA 660/3 74 020
August 1974
                                   Ecological Research Series
    Estimating Nutrient Loadings
    of Lakes from Non-Point Sources
                                Office of Research and Development

                                U.S. Environmental Protection Agency
                                Washington, D.C. 20460


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                                       EPA-660/3-74-020
                                       August 1974
ESTIMATING NUTRIENT  LOADINGS  OF LAKES

         FROM  NON-POINT SOURCES
                       by
                 Paul D.  Uttormark
                  John D. Chapin
                 Kenneth  M. Green
              Water Resources Center
             University of Wisconsin
             Madison, Wisconsin 53706
                Program Element 1BA031
                 Roap/Task 21 AJE 28
                  Grant R-801343
                  Project Officer
                 Thomas E.  Maloney
       National Environmental  Research Center
              Corvallis, Oregon 97330
                   Prepared for

          OFFICE OF RESEARCH AND MONITORING
        U.S.  ENVIRONMENTAL PROTECTION AGENCY
              WASHINGTON, D.C. 20460

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                          ABSTRACT
Data describing nutrient contributions from non-point sources
were compiled from the literature, converted to kg/ha/yr,  and
tabulated in a format convenient for estimating nutrient
loadings of lakes.  Contributing areas are subdivided accord-
ing to general use categories, including agricultural, urban,
forested, and wetland.  Data describing nutrient transport by
groundwater seepage and bulk precipitation are given along with
data for nutrient contributions from manure handling, septic
tanks, and agricultural fertilizers.

Nutrient content of urban runoff was the highest; forested
areas were lowest.  Nutrient export data for agricultural lands
were tabulated as:  seepage through vertical soil profile,
overland runoff, and transport by streams draining agricultural
watersheds.  The latter group was judged to be most applicable
for estimating nutrient loadings of lakes.  Marshes appear to
temporarily store phosphorus and nitrogen during the growing
season and release them at a later time; net nutrient runoff
is estimated to be near zero.  Nutrient contributions to lakes
from groundwater seepage require site-specific information for
assessment.  Phosphorus and nitrogen transport by groundwater
can be significant.  Atmospheric contributions of nitrogen are
large in some areas.

The technique of estimating nutrient loadings of lakes requires
considerable judgment in selecting runoff coefficients; however,
the approach provides insight into potential management options.

This report was submitted in fulfillment of Grant R-8013U3 by
the University of Wisconsin under the sponsorship of the
Environmental Protection Agency.  Work was completed as of
June 197H.

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                          CONTENTS
                                                      Page
Abstract                                               ii
List of Figures                                        iv
List of Tables                                          v
Sections
I      Introduction                                     1
II     Nutrient Sources and Transport Vectors           6
         Nutrient Sources                               6
         Contributing Areas                             7
III    Nutrient Export from Agricultural Lands         13
         Fertilizers                                   14
         Nutrient Losses by Seepage                    19
         Surface Runoff from Agricultural Lands        24
         Nutrient Transport by Streams
         Draining Agricultural Lands                   29
         Manure Handling                               40
IV     Nutrient Export from Urban Areas                48
         Factors Contributing to the Nutrient
         Content of Urban Runoff                       51
V      Nutrient Export from Forests                    55
VI     Nutrient Losses from Marshes and Wetlands       60
VII    Nutrient Influx from Groundwater                62
VIII   Nutrient Contributions from Septic Tanks        71
IX     Atmospheric Contributions
       of Nitrogen and Phosphorus                      74
         Factors Affecting Nutrient Content
         of Bulk Precipitation                         74
         Cartographic Presentation of Nitrogen
         Contributions from Precipitation              78
X      Summary                                        100
                             111

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                           FIGURES


No.                                                   page


1    Subdivision of Drainage Basins                     10
2    Nitrogen Contributions (N03-N S
     from Rainfall                                      87

3a   Format for Comparing Nutrient Runoff
     Coefficients                                      103

3b   Nutrient Export from Urban Areas                  104

3c   Nutrient Export from Forested Lands               105

3d   Nutrient Export from Agricultural Lands           106
                              IV

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                           TABLES
No.
 1   Specific Loading Levels for Lakes Expressed
     as Total Nitrogen and Total Phosphorus
     in g/m2/yr                                         2

 2   "Natural" Modes of Nutrient Transport to Lakes     7

 3   Annual Loss of N, P, and Suspended Solids in
     Tile Drainage Water, Woods lee, Ontario            15

 4   Nutrient Export in Surface Runoff from
     Experimental Plots--Sediment and Water Fractions  17

 5   Effect of Crop Cover and Slope on Nutrient
     Export via Surface Runoff                         18

 6   Nutrient Export from Croplands by Seepage
     through Soil Profile                              25

 7   Nitrate Export from Croplands by Surface Runoff   30

 8   Nutrient Export from Croplands by Surface
     Runoff                                            31

 9   Nutrient Transport from Agricultural
     Watersheds by Streams                             36

10   Nutrient Characteristics of Manure from
     Domestic Animals                                  m

11   Export of Nutrients from Urban Areas              49

12   Average Nutrient Concentrations in Urban Runoff   52

13   Nutrient Export from Forested Watershed
     via Streamflow                                    58

14   Nutrient Contributions to Lakes via Groundwater   63

15   Partial List of Methods for Investigating the
     Groundwater-Surface Water Interchange             65
                              v

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16   Groundwater Contributions to the Water Budget
    . of Lakes                                           66

17   Atmospheric Contributions of Nitrogen              79

18   Atmospheric Contributions of Phosphorus            83

19   Influence of Local Conditions on Nutrient
     Contributions from the Atmosphere                  89

20   Typical Values of Nutrient Runoff Coefficients     108

21   Direct Drainage Areas for Selected Wisconsin
     Lakes                                             109

22   Conversion Factors                                112
                             vx

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                        INTRODUCTION
Eutrophication is a natural process which affects lakes
at different rates.  Some lakes are relatively unaffected
by natural factors which have been operating for thousands
of years.  Others have passed through advanced stages of
eutrophication and are now extinct.  Although eutrophication
is often described as an aging process, it is important to
realize that the process is not necessarily unidirectional—
reversals are possible and do occur.

It has been known for years that the natural process of
eutrophication can be accelerated by the activities of
people.  Analyses of lake sediment cores have been used to
document this observation.  The exact mechanisms by which
the activities of people influence the rate of eutrophica-
tion have been identified only in general terms, but it is
reasonable to assume that land use practices are a signifi-
cant factor because they alter the pathways and rate of
nutrient transport from the landscape.

Mounting concern for maintaining water quality in, lakes and
controlling the undesirable effects of eutrophication has
emphasized the need for quantitative information concerning
the nutrient budgets of lakes.  It is generally agreed that
the most desirable long-term lake management approach is to
control, insofar as is possible, the influx of nutrients,
although there is considerable disagreement regarding the
selection of nutrient sources which should be controlled,
the method for control, and the benefit which is to be
gained.  In particular, the complex internal nutrient cycles
involving lake sediments have been identified as factors
which could potentially negate the beneficial effects of
reducing external inputs of nutrients.  Nevertheless, even
though a drastic reduction of the nutrient input may not
alone be sufficient to attain the desired level of water
quality in all instances, nutrient abatement is an essential
component of management efforts.  Regardless of internal
nutrient cycles, water quality improvement will not result
if the continuous influx of nutrients is excessive.

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The intricate process of eutrophication is far too complex to
expect that simple relationships can be established between
the influx of nutrients and undesirable plant production or
other parameters of lake quality.  Yet, sufficient information
does exist to provide some guidelines.

On the basis of water analyses from 17 Wisconsin lakes, Sawyer
(1947) suggested that if, at time of spring overturn, concen-
trations of inorganic phosphorus and inorganic nitrogen (am-
monia plus nitrate nitrogen) exceeded 0.01 mg/1 and 0.3 mg/1
respectively, a lake may be expected to produce excessive
growths of algae or other aquatic plants.  Vollenweider (1968)
statistically analyzed data reported by Thomas (1953) and con-
cluded that the critical levels suggested by Sawyer were
generally borne out by the conditions of lakes in central Europe.

These critical concentrations, although not rigid lines of
demarcation, do provide target values for lake improvement
and protection.  However, it is difficult to relate these
values directly to reductions in nutrient input, because the
relationship between nutrient influx and in-lake nutrient
concentrations is poorly understood.

Tentative guidelines for relating the nutrient influx to water
quality in lakes are provided by criteria presented by Vollen-
weider (1968).  The surface area of the lake is taken into
account by expressing nutrient influx as a specific loading
rate (g/m^/yr).  Residence times are not included in these
guidelines, but the effect of lake volume is included because
permissible rates of specific loading are greater for lakes
of larger mean depth.


    Table 1.  SPECIFIC LOADING LEVELS FOR LAKES EXPRESSED
      AS TOTAL NITROGEN AND TOTAL PHOSPHORUS IN g/m2/yra


                      Permissible    Dangerous loading
      Mean depth    loading, up to:    in excess of:
        up to:       N

           5 m      1.0

          10 m      1.5

          50 m      4.0

         100 m      6.0

         150 m      7.5

         200 m      9.0

      afrom Vollenweider (1968)

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These results are based on data from 30 lakes (12 from
central Europe, 10 from North America, and 8 from northern
Europe) and must be considered to be provisional guidelines
which require confirmation or modification by subsequent
work.  Nevertheless, they do provide criteria for assessing
the need for nitrogen and phosphorus abatement and the poten-
tial benefits to be realized in specific situations.  Shannon
and Brezonik (1972) conducted a somewhat similar analysis of
nutrient loadings of 55 lakes in Florida and reported per-
missible areal loadings of 2.0 and 0.28 g/m2/yr and critical
loadings of 3.4 and 0.4-9 g/mVyr for nitrogen and phosphorus
respectively.

Refinement of these criteria and the determination of their
regional applicability are dependent on the availability of
valid nutrient loading information for numerous lakes repre-
senting a spectrum of trophic character.  Ideally, these
nutrient loadings would be determined by direct measurement;
potentially significant sources would be identified and
their contributions would be documented.  However, because
the costs associated with this course of action are prohibi-
tive in most situations, it is necessary that less costly
techniques be developed for use in assessing management
alternatives and  establishing priorities.  In recent years,
the technique of  estimating nutrient  loadings has been used
in a number of situations as  a guide  for management decisions,
The primary objective  of this report  is to compile nutrient
flux data derived from the  scientific literature and present
it in  a format applicable to  the  estimation  of nutrient  load-
ings for lakes.   This  report  deals primarily with diffuse
nutrient sources, and  data  are presented which may be used
to estimate nutrient influx to lakes  via various transport
mechanisms.  It  is  intended to provide  data  for  predicting
the  quantities of nutrients which enter lakes; questions
relating to the  ultimate  availability of these nutrients are
not  addressed  directly.

Nutrient availability  in  aquatic  environments encompasses ^
several considerations.   Chemical form is  important.  It is
known  that many  algal  species  can utilize  both nitrate  and
ammonia nitrogen, and  some  bluegreen  algae can use  molecular
nitrogen as well.  Orthophosphate is  generally considered
to be  the form of phosphorus  most readily  utilized.

Transport processes  also  influence nutrient  availability in
aquatic systems.   In addition to  being in  a  usable  chemical
form,  nutrients  must come into physical proximity of  plants
at a time when they can  be  used.   Therefore,  the ultimate

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availability of nutrients depends not only upon their chemical
form upon entry to a lake, but also upon subsequent chemical
transformation and transport.  Such considerations are clearly
beyond the scope of this work.

The approach used in this study was to provide data in a
format applicable for the estimation of loadings based on
either inorganic or total forms of nitrogen and phosphorus.
In many practical situations it will be advantageous to pre-
pare an estimate for both total and inorganic loadings—the
latter as an indication of the quantity of nutrients which
are immediately available, and the former as a conservative
estimate of the amounts which could ultimately become avail-
able.

To achieve the objectives of this report, it was necessary
to convert data presented in a variety of forms into a more
usable and consistent format.  The units selected were:
kg/ha/yr for transport from land areas, kg/ha of lake surface/
yr for aerial influx, and kg/capita/yr or similar units for
point source contributions.  The most common difficulties
encountered in accomplishing these transformations related
to the identification of the chemical species reported and
the analytical procedures by which the chemical determinations
were made.  This problem was compounded by differing sample
pretreatment--some are filtered, some are not; and often these
details are not given at all.  An attempt was made to be
rigorous but, in some instances, it was necessary to make
assumptions in order to present the data in a consistent
format.  Also, in a few cases, data which were collected for
only portions of years are included in the tables.  Readers
are cautioned to examine the footnotes for clarifying or
restricting information.

The following terminology is used in this report:

total phosphorus:  All forms of phosphorus, whether dissolved
     or in suspension, that are measured by an acid-oxidation
     procedure.
total, dissolved phosphorus:  The amount of phosphorus deter-
     mined by an acid-oxidation procedure after sample
     pretreatment with 0.45 ym filtration.
dissolved inorganic phosphorus:  The quantity of phosphorus
     as determined by a procedure for inorganic orthophos-
     phorus after sample pretreatment with O.M-5 ym filtration.

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total nitrogen:   All forms of nitrogen in a sample, dissolved
     or suspended, including NH^-N, N03-N, N02-N, and organic-N,

organic nitrogen:  Quantity of nitrogen (as NH^-N) determined
     by Kjeldahl digestion.


REFERENCES

Sawyer, C. N.   1947.  Fertilization of Lakes by Agricultural
     and Urban Drainage.  New England Water Works Assoc. J.
     _6K2):109-127.

Shannon, E. E.,  and Brezonik, P. L.  1972.  Relationships
     between Lake Trophic State and Nitrogen and Phosphorus
     Loading Rates.  Environ. Sci. Techno1. _6:719-725.

Thomas, E, A.   1953.  Empirische und experimentslie Unter-
     suchungen zur Konntnis der Minimumstoffe in 46 Seen der
     Schweiz.  und angrenzonder Gebiete.-Schweiz. Ver. Gas &
     Wasserfachm. _2_:3_~IL5.

Vollenweider,  R. A.  1968.  Scientific Fundamentals of the
     Eutrophication of Lakes and Flowing Waters} with Par-
     ticular Reference to Nitrogen and Phosphorus as Factors
     in Eutrophication.  Pub. No. DAS/CSI/68.27, Organisation
     for Economic Co-operation and Development, Directorate
     for Scientific Affairs, Paris, France.

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           NUTRIENT SOURCES AND TRANSPORT VECTORS
NUTRIENT SOURCES

In considering the flow of nutrients across the landscape it
becomes clear that, in a strict sense, there are no sources
or sinks, but rather, there exists a multitude of cyclic
pathways along which nutrients are transported.  In this
context, "sources" are simply points along the nutrient flow
paths which are designated for convenience.  Throughout this
report, an attempt has been made to incorporate the concept
of potential management or control in the designation of
nutrient sources and, also, to distinguish between sources
and transport vectors.  Toward this end, the following defi-
nitions were developed:

nutrient sources:  Sites at which plant nutrients are released,
     or areas from which nutrients are exported, and subsequent
     transport is determined by uncontrolled natural mechanisms,

point source:  A location at which nutrients are released in
     quantity and concentration compatible with practical
     means of nutrient removal.  (example: sewage effluent)

diffuse source:  An area from which nutrients are exported
     in a manner not compatible with practical means of
     nutrient removal.  (example: croplands)

specific contributor:  Materials or products containing
     nutrients which are discarded or used in a manner such
     that the nutrients contribute to point or diffuse
     sources.  (example: detergents, fertilizers)

In the context of these definitions, groundwater, precipitation
and dry fallout (dust fall) are treated as transport vectors,
not sources of nutrients.   Urban runoff is treated here as an
export from a diffuse source although it is recognized that
in many situations this runoff is collected in storm sewer
systems and that practical means of nutrient removal may be
applied in some cases.

From the standpoint of nutrient control or abatement, manage-
ment action can usually be most readily applied to point
sources and specific contributors.  Both technological and

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regulatory approaches can be used.  Control of nutrient
transport from diffuse sources is generally aimed toward
reducing the efficiency of transport mechanisms (for example,
contour farming to minimize runoff from agricultural lands).

The concepts of pathway definition and mode of transport
are particularly important for estimating nutrient flux from
diffuse sources because nutrients may be exported simul-
taneously along many pathways and can be transported by
several mechanisms.  For example, soil particles from a given
area could become airborne and reach a lake via dry fallout
or precipitation.  Storm runoff could transport nutrients
overland to an inflowing stream, or rainwater could percolate
through the soil profile to the groundwater aquifer and sub-
sequently enter a lake directly or through the base flow
of tributary streams.  Waterfowl could feed in a field and
deposit nutrients in a lake.  These are just a few of many
potentially significant modes of transport.
CONTRIBUTING AREAS

Table 2 gives a listing of transport mechanisms for nutrients,
points of entry to a lake, and the land areas which contribute
nutrients via the various modes of transport.  It is apparent
from this tabulation that, with respect to a particular lake,
the land areas contributing nutrients are not identical for
all modes of transport.  Nutrients contained in rainfall may


  Table 2.  "NATURAL" MODES OF NUTRIENT TRANSPORT TO LAKES
Mode of transport

Groundwater

Surface water
 a) streamflow
 b) streamflow
 c) overland flow

Precipitation

Dry fallout

Miscellaneous
 a) waterfowl
 b) N-fixation
Entry to lake

  land-water
  interface
inlet streams
inlet streams
lake perimeter

 lake surface

 lake surface


 lake surface
    Contributions from
unknown portion of ground-
   water drainage basin


  direct drainage basin
 indirect drainage basin
immediately adjacent lands

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have been transported for great distances through the air
before returning to earth, and the area contributing these
nutrients defies description.  A similar situation exists
for other transport mechanisms which involve air pathways.

Lands contributing nutrients to shallow groundwater aquifers
can be defined more clearly since boundaries of groundwater
basins are often approximately the same as the surface drainage
basins.  However, it is not necessary that all groundwater
leaving the basin pass through the lake and, since the extent
of communication between ground and surface waters is often
poorly defined, it is extremely difficult to determine that
portion of the total groundwater basin actually contributing
water to a lake.  Contributing lands can only be defined with
reasonable certainty when surface water transport is considered.

Even if all lands within a lake's drainage basin are taken
into account, it is clear that 1) it is not necessary that all
nutrients exported from the land ultimately reach the lake
and, conversely, 2) it is not necessary that those nutrients
which are transported to a lake originate from sources within
the drainage basin.  The nature of the situation dictates that
estimates of nutrient input from diffuse sources be based on
considerations of the transport mechanism involved, and nutrient
sources are taken into account only indirectly.  Also, land
use characteristics can only be related directly to nutrient
transport to lakes via surface water flows.  Lack of definition
of contributing areas prohibits the application of land use
data to other modes of transport.


Contributing Areas - Surface Water Transport

For purposes of estimating nutrient flux from watersheds , it
is often convenient to subdivide the topographic drainage
basin into two or possibly three units:  the direct drainage
basin, the indirect basin, and immediately adjacent lands.
This latter category is of lesser importance, and would
probably be used only in special situations.  Small lakes
with highly-developed shorelines may be one situation where
this delineation would be advantageous.

The direct drainage basin is defined as that portion of a
lake's drainage basin which does not drain to upstream lakes
or impoundments.  The indirect basin(s) include all lands
draining to lakes upgradient from the lake in question.  These
lakes may or may not have surface water outlets.  Immediately
adjacent lands are a part of the direct basin and are defined
as those areas from which runoff drains overland directly to
a lake without entering a stream.

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An illustration of these basin divisions is given in Figure 1.
Two indirect basins are shown in the sketch, but only one
contributes surface water to the lake below.
Indirect drainage basin

By definition, if surface waters cross the boundary between
indirect and direct drainage basins, the transfer occurs only
at the outlet of a lake.  All water flowing from the indirect
drainage basin must first pass through a lake, which is not
only a point of concentration for flow, but is also a dis-
continuity in the nutrient pathway.  It is known that, in
general, lakes act as partial nutrient traps; more nutrients
are received than are discharged.  Therefore, a lake is a
buffer which retards nutrient flow and protects downstream
waters from the influence of lands above.  If the lake has no
outlet stream, the drainage basin contributes no nutrients via
surface water to lakes below.

In view of the difficulties involved in defining the flow of
nutrients through lakes, it is most convenient to treat the
lake outlet as a point source which incorporates the contri-
bution from all lands upstream.  This approach requires that
the volumetric rate of outflow and the corresponding nutrient
concentrations be determined or  estimated, but avoids the
necessity of  defining land use practices throughout the basin
and estimating the efficiency with which the  lake inhibits
nutrient passage.

In most instances, it is desirable to determine mean flowrates
and nutrient  concentrations on a seasonal basis which corre-
sponds to the thermal regimen of the lake.   For deep lakes
in temperate  zones, four periods should be considered to
account for:  ice cover, spring  overturn, summer stratifica-
tion, and fall overturn.  Ideally, both flow  data and nutrient
data would be available for the  lake in question.

Many lakes have control structures at the outlet.  Some have
a fixed sill which acts as a broadcrested weir and, if water
level elevations are recorded, the rate of outflow can be
computed with reasonable accuracy.  Others have release gates
which are manipulated to regulate outflow, and in these situa-
tions flow records are often maintained.  Streamflow records
at some point in the channel downstream may  also be used if
they are adjusted to account for inflow received below the lake,

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f   N
\
                            X
     V
                      Direct
                       Drainage
                         Basin
           i
                                           /
f
i*



/
1
-"I
•
/
/
/


                                      Immediately
                                      Adj acent
                                      Lands
  Figure  1.   SUBDIVISION OF DRAINAGE BASINS
                    10

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If flow records are not available, it is possible to synthesize
the outflow hydrograph from rainfall-runoff relationships.  By
estimating that portion of total precipitation which results
in runoff, and accounting for storage in snow cover, reasonable
estimates of total discharge for the selected time periods can
be prepared.  A technique such as this does not yield accurate
results for short time periods, but is adequate to describe the
average total discharge that might be expected to occur during
a period of several months.

In those situations where lake releases are controlled by outlet
structures, it is important to establish the depth from which
waters are discharged because this may have a significant effect
on both the quantity and form of nutrients which are released.
Dunst, Wirth and Uttormark (unpublished data) found that  con-
tinuous hypolimnetic discharge increased the total amount of
phosphorus and nitrogen released from a small impoundment in
southwestern Wisconsin by 22% and 25% respectively as compared
to nutrient output via a surface spillway.  Furthermore,  during
periods of stratification, the majority of nitrogen and phos-
phorus in  the hypolimnetic discharge waters was in readily
available  forms—NH^-N and dissolved inorganic-P.  In contrast,
nutrients  contained in waters released  from the surface of lakes
are  often  in  forms not readily available to aquatic plants.


Immediately adjacent  lands

Because  of their proximity,  shorelands  have a greater potential
for  contributing nutrients to  lakes than lands which lie  in
remote portions of the drainage  basin.  Therefore,  in those
situations where shorelands  are  devoted to uses which result
in high  rates  of nutrient  flux,  it may  be  desirable to  treat
these lands separately for purposes of  loading calculations.
For  example,  it is reasonable  to assume that particulate  forms
of nutrients  exported from shorelands will be transported to
the  lake,  whereas  this is  far  less likely  for distant lands.
Lakes surrounded by flat,  forested areas with extensive ground
cover probably receive only  minor contributions  from immediately
adjacent  lands, and delineation  of these areas is probably not
important.  In contrast, the contribution  to some lakes,  par-
ticularly  impoundments formed  in steep-sided valleys surrounded
by cultivated farmlands, could be considerable,  and separate
consideration of these areas would be  justified.  This  may  also
be the case for lakes which  are  surrounded by residences  where
lawns are  maintained.
                              11

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REFERENCE
Dunst, R. C., T. L. Wirth, and P. D. Uttormark.   1974.   Effect
     of Bottom Water Discharge upon the Limnology of a
     Reservoir.  Wisconsin Dept. of Natural Resources,  Madison,
     Wis.
                              12

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           NUTRIENT EXPORT FROM AGRICULTURAL LANDS


The transport of nutrients from agricultural lands to lakes
could occur along innumerable pathways and could involve many
transport mechanisms.  For purposes of this report, water is
considered to be the primary transport vector, although it is
recognized that nutrient loss by wind-blown particulate matter
could be large in some instances.

Three data groupings were prepared which describe the flux of
nitrogen and phosphorus from agricultural lands:  1)_seepage
studies, 2) runoff  studies and  3) drainage area studies.  The
first two study types refer to  the transport of nutrients
across the boundaries of land areas.  The latter type refers
to  nutrient transport by continually  flowing.streams.  It is
important to recognize that only  a few of the investigations
cited were conducted to quantify  nutrient runoff  from water-
sheds to lakes.  The objective  of most studies was to measure
nutrient loss  from distinct land  parcels.  Therefore, ques-
tions of subsequent nutrient transport must be  addressed before
the data can be used for  estimating nutrient  contributions  from
agricultural lands.

Seepage  studies include  lysimeter work and  analyses  of  tile-
drained  fields.   Data  from these investigations  may  be  useful
in estimating  the  transport of nutrients  from surface  soils
to groundwater aquifers,  but  the applicability of these results
to the estimation of lake  loadings  depends  greatly on  the
extent of  groundwater-surface  water exchange  in the  basin
under consideration.

Losses of  nutrients by storm runoff have  been quantified in
a number of  studies.  However, the ability to predict_nutrient
loadings  from these data is again limited by the difficulty
in defining  the probability of transport  from agricultural
 lands  to lakes.   This  difficulty is amplified by the fact
that a large portion of the nutrients lost from agricultural
 lands  is  associated with particulate matter which may_settle
 out at  intermediate points along the flow path, especially
 during  overland flow or in intermittent  stream channels.

 From the standpoint of lake loadings, some of the most useful
 data are provided by drainage  area studies because of  the
                              13

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clearly defined  pathway for nutrients contained in continually-
flowing streams.  However, some trade-offs are involved.  Land
use patterns are defined clearly for most seepage and runoff
studies , but subsequent transport of nutrients to a lake is
questionable.  In contrast, nutrient flow paths are more
clearly defined for drainage area studies, but descriptions
of land use are very imprecise (i.e., "typical rural environ-
ment" or "mixed farmlands and woodlots").
FERTILIZERS

Large quantities of commercial fertilizers are applied annually
to agricultural lands throughout the United States.  Typical
application rates range from 20-200 kg N/ha and from 10-50 kg
P/ha.  Because of the large amounts used, fertilizers have often
been singled out as potentially important contributors to lake
eutrophication.  Although many studies have been conducted and
much has been written, it is difficult to assess the importance
of nutrient runoff from fertilized croplands because many
determining factors are site-specific and, in addition, pre-
cipitation characteristics are important.

The application of fertilizers increases the amount of nutrients
which could potentially be lost from agricultural lands, but
offsetting factors have been shown in some instances to more
than compensate for the increased potential.  Proper applica-
tion, which includes matching the quantity and composition of
fertilizer to crop needs and soil fertility, can reduce the
amount of nutrient loss from croplands by increasing nutrient
utilization by plants, and by increasing crop density which
reduces surface runoff and erosion.  Conversely, if the addition
of fertilizers creates a nutrient imbalance, or if excessive
rainfall occurs shortly after application, nutrient losses can
be large.

Taylor et al (1971) compared the additions of fertilizers to
farmlands (near Coshocton, Ohio) to the subsequent nutrient
loss via runoff, and found no relationship between the two.
They identified variations in water flow as the most signifi-
cant variable determining nutrient loss.

Similar results were reported by Kilmer et al (1971) from
studies of two watersheds in North Carolina where fertilizer
applications to bluegrass sod were evaluated.  During the first
two years of a three-year study, about 10 kg/ha per year more
nitrogen was lost from the fertilized watershed than from the
unfertilized watershed (fertilizer applied at 112 kg N/ha).

-------
However, during the third year, fertilizer was applied to both
watersheds and reduced levels of nitrogen loss were noted; in
fact, the nitrogen loss from the watershed receiving fertilizer
for the first time was less than for either of the two years
when no fertilizer was used.

In general, the deep seepage loss of nitrogen is the major
export pathway from agricultural lands.  Both nitrate and
ammonium are mobile in soil systems and are readily trans-
ported by seepage water.  Zwerman et al (1971) reported that
seepage losses of nitrogen may be as high as 225 kg/ha/yr.
Runoff losses were reported to be generally small except in
those instances when heavy rainfall occurred immediately after
fertilizer application.

Phosphorus, unlike nitrogen, is not particularly mobile within
the soil, and phosphate ions do not leach readily.  Phosphorus
is held tightly as a complex anion by clays, and the amount of
phosphate in solution in the soil water at any one time is small.
Most phosphorus is removed from soil systems by either crop
uptake or soil erosion.  Soil  erosion can be diminished by using
sound conservation practices such as increasing soil aggregation
by the  addition of organic residues and providing cover crops
to reduce the impact of rainfall and erosion.

Data showing an increase in annual loss of nitrogen and phos-
phorus in tile drainage water  from fertilized crops was pre-
sented by Webber and Elrick  (1967) (Table 3).  Drainage effluent

     Table 3.  ANNUAL LOSS OF  N, P, AND SUSPENDED SOLIDS
         IN TILE DRAINAGE WATER, WOODSLEE, ONTARIO^
N (kg/ha)

Bluegrass sod
Continuous corn
Corn (rotation)
Alfalfa (2nd yr)
No
fert
0.2
5.7
4.6
4.9
Fertb
0.2
11.9
11.5
5.7
Suspended solids
P (kg/ha) (kg/ha)
No
fert
0.01
0.19
0.10
0.07
Fert
0.02
0.21
0.15
0.18
No
fert
15.5
93.0
30.7
29.5
Fert
29.7
84.0
38.0
33.5
afrom Webber and  Elrick  (1967)
b335 kg/ha  5-20-10  fertilizer  applied  for  all  crops  each  year
 plus 110 kg N/ha on  the  corn.
                              15

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from a tiled area of Brookston clay at Woodslee, Ontario was
analyzed over a 6-year period (1961-1966).  Average annual
nitrogen losses ranged from 0.2 kg/ha under bluegrass sod
to 11.9 kg/ha under fertilized continuous corn.   Average phos-
phorus loss ranged from 0.01 kg/ha/yr (unfertilized bluegrass
sod) to 0.21 kg/ha/yr (fertilized continuous corn).

Timmons, Burwell and Holt (1968) analyzed the water and sedi-
ment fractions of runoff samples from experimental plots near
Morris, Minnesota.  (See Table 4.)  The 0.009 ha plots were
on loam soil at 6% slope.  Crop residues were left on plots
following harvest and some fertilizer was applied.  Except for
the plots of hay, 78-94% of the nitrogen lost in surface runoff
was associated with particulate matter, and nitrogen loss in-
creased as the density of crop cover decreased.   The same
general trend is shown for phosphorus loss, but a smaller
portion of the total amount exported is contained in the sedi-
ment fraction.  These results illustrate the importance of
erosion control for minimizing nutrient loss from croplands.

Table 5 gives data presented by Eck (1957) which show some
effects of slope and crop cover on the loss of nitrogen and
phosphorus in surface runoff of selected test sites.  In
general, nutrient export increased as the slope increased
(different soils types, however), and more nutrients were lost
from row crops than from cover crops.  The ratio of N/P in the
runoff water was more dependent on soil type than crop cover.

Although this study and the one conducted by Timmons et al
(1968) were not designed to evaluate the effects of fertilizer
use directly, they do illustrate the importance of erosion
control and crop density—factors which can be influenced
significantly by fertilizer use.

Holt et al (1970) presented data showing increased nutrient
concentrations in runoff from fertilized land as compared to
an unfertilized control, and also the importance of incorpor-
ating fertilizers into the soil.

                                     Total phosphorus
       Fertilizer j/pplication        (mg/1) in runoff

       Control (no fertilizer)             0.08
       Broadcast  and plowed under          0.09
       Broadcast  and disked in             0.16
       Broadcast  (no soil treatment)       0.30
                              16

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        Table 4.    NUTRIENT EXPORT
IN SURFACE RUNOFF FROM EXPERIMENTAL PLOTS--
       SEDIMENT AND WATER FRACTIONSa
Crop
Hay:
sediment
water
total
Oats :
sediment
water
total
Corn ( 1 ) :
sediment
water
total
Corn ( 2 ) :
sediment
water
total
Fallow:
sediment
water
total •
Total-N
kg/ha/yr
0.0
3.5
3.5
5.2
0. 8
6. 0
4.3
1.2
5.5
13.
0.8
13.8
63
3.9
66.9
Total-P
% kg/ha/yr %
0
100
100
87
13
100
78
22
100
94
1
100
94
6
100
0.0
0.23
0.23
0.03
0.01
0.04
0.04
0.07
0.11
0.11
0.07
0.18
0.34
0.05
0. 39
0
100
100
75
25
100
36
64
100
61
__3i
100
87
13
100
Fertilizer applied:
  corn  (1)        56 kg N/ha
  corn  (2)       112 kg N/ha
  oats            18 kg N/ha

aBased  on Timmons, Burwell and Holt  (1968)
29 kg P/ha
29 kg P/ha
30 kg P/ha
                    17

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         Table 5.  EFFECT OF CROP COVER AND SLOPE
          ON NUTRIENT EXPORT VIA SURFACE RUNOFFa
Crop
Corn
Oats
Corn
Oats
Wheat
Tobacco
Corn
Oats
Corn
Oats
Hay
Slope
%
3
3
8
8
8
8
11
11
20
20
20
Soilb
A
A
M
M
M
M
F
F
F
F
F
N
kg/ha/yr
18.
8.1 '
21.
7.7
0.9
49.
8.9
35.
42.
38.
3.3
PC avail)
kg/ha/yr
0.48
0.21
0.52
0.24
0 .04
2.1
0.64
• 1.8
2.0
1.7
0.26
N/P
37
39
40
32
22
23
14
19
21
22
13
after Eck (1957)

A - Almena silt loam
M - Miami silt loam
F - Fayette silt loam
                            18

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Other studies have demonstrated that proper use of fertilizers
in concert with good plowing practices reduces nutrient loss
because of increased crop cover and reduced erosion (Neal,
1944; Weidner et al, 1969; Minshall et al,  1970).  Positive
correlations between fertilizer additions and nutrient loss
were reported by Bolton et al (1970 , Broadbent and Chapman
(1950), Hendrick and Welsh (1938), and Dreibelbis (1946).
Because of the complexities involved and the differing results
reported in the literature, no attempt is made in this report
to separate data on the basis of fertilizer usage.  However,
the practice of spreading manure on farmlands is treated
separately later in this chapter.


NUTRIENT LOSSES BY SEEPAGE

Nutrient loss from agricultural lands by seepage through the
soil profile has been a topic of interest for several decades.
The majority of the earlier studies were conducted to evaluate
alternative agricultural practices, such as, crop rotation,
fertilizer usage, and plowing techniques, and losses of nitrate
nitrogen were studied almost exclusively.  In more recent years,
emphasis has been placed on evaluating the effects of agricul-
tural practices on water quality,  and losses of phosphorus as
well as nitrogen have been reported.

Two types of studies are reported  in the literature which
describe the transport of nutrients by seepage through soils.
These involve the use of lysimeters or the analysis of waters
which flow from tile-drained croplands.

Lysimeters are constructed by surrounding a  volume of earth
on the sides and bottom with an impermeable  material.  The en-
closed soil is more or less disturbed, depending  on how it is
placed in the enclosure.  The top  is  exposed to  the elements,
and drains are connected to the bottom,  so that  all water
percolating through the soil profile  can be  collected and
analyzed.  Runoff and erosion are  generally  prevented by the
design of the unit.  Surface areas of these  units range from
0.1 to 10m2, and it is reported that  some units  have been
maintained actively for periods as long  as  35 years.

In some parts of the country, particularly those  regions in
which irrigation is practiced, large  tracts  of  land are
underlain with tiles or other subsurface collection systems.
Some of the  irrigation water percolates  through  the soil
profile and  is removed by these drainage systems.  A number of
studies have been reported in which drainage waters were sampled
                              19

-------
periodically and analyzed for nitrogen and phosphorus to
measure nutrient losses.  In many respects, studies of this
type are similar to lysimeter studies, but the surface areas
covered are much larger, and not all of the seepage water is
collected--some is lost to deeper aquifers.

The data from seepage studies presented in this section are
grouped according to crop, but crop cover plays only a partial
(and possibly minor) role in influencing nutrient loss.

Bolton, Aylesworth, and Hore (1970) measured nutrient losses
in tile drainage effluent from twelve 0.1 ha plots at Woodslee,
Ontario (clay soils).  Seepage flows were recorded continuously,
and effluent samples were filtered to remove sediment and
analyzed for total nitrogen and phosphorus.  The authors con-
cluded that the nutrient loss was influenced predominantly by
the amount of water that percolated through the soil.
                                Nutrient loss (kg/ha/yr)
                                 N                  P
  Crop
Rotation:

  Corn

  Oats and alfalfa

  Alfalfa, 1st year

  Alfalfa, 2nd year

Continuous:
No fert


  5.6

  4.3

  4.8

  4.7
Fert


15.1

 5.7

 3.9

 8.6
No fert


  0.13

  0.13

  0.13

  0.08
Fert


0.24

0.13

0.15

0.22
Corn
Bluegrass sod
Mean:
6.6
0.3
(4.4)
14.0
0.7
(8.1)
0.26
0.01
(0.12)
0.29
0,12
(0.19)
after Bolton, Aylesworth, and Hore (1970)

In contrast, Sylvester and Seabloom (1962) monitored irrigation
return flows in the Yakima Valley in Washington and found that
more nitrate and soluble-P were lost during the 6-month non-
irrigation period than during the irrigation season even
though 130 cm of water were applied (average rainfall was
18 cm/yr).  The return flow consisted of both surface runoff
and seepage through subsurface drains which continued to flow
during the non-irrigation season.  Samples were collected and
analyzed for nitrate, total Kjeldahl nitrogen, and dissolved
and total phosphorus.  This project was also described by
Sylvester (1961) and separate results are given for surface
and subsurface drains.
                             20

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                     Irrigation
                       season
                             Nutrient loss __(kg/ha)
Non-irrigation
    season
   Nitrate-N            34.             39.

   Dissolved-P           0.78           1.7

   after Sylvester and Seabloom (1962)
Annual

 73.

  2.5



Surface drains
Subsurface drains
Nutrient loss
Total-N
Range Mean
2.8-27 (16)
61-186 (103)
(kg/ha/yr)
Total-P
Range Mean
1.0-4.4 (2.5)
3.8-10 (7.7)
   after Sylvester (1961)

Studies in which nutrient losses from croplands by tile drain-
age were compared to losses via surface runoff were also con-
ducted in California and Idaho.

Johnston, Ittihadieh, Daum and Pillsbury (1965) analyzed tile
drainage effluent and surface runoff from irrigated land in
the San Joaquin Valley of California.  Four 19- and 60-ha plots
growing cotton, alfalfa and rice were studied.  The soils were
heavy silty clays, and tile depth averaged 190 cm.  Analyses
                        Nutrient loss
                           kg/ha/yr
         Fertilizer applied
             kg/ha/yr
Crop
Cotton and rice
Tile drainage
Surface runoff
Cotton
Tile drainage
Surface runoff
Alfalfa
Tile drainage
Surface runoff
Rice
Tile drainage
Surface runoff
Total-N

110 .
11.

13.
6.4

3.5
1.6

42.
5.2
Total-P

0.19
0.81

0.05
0.17

0.08
0.20

0.60
0.11
N P
300 52


220 36


none none


94 none


after Johnston, Ittihadieh, Daum and Pillsbury (1965)
                              21

-------
were made for total nitrogen and total phosphorus.   No esti-
mates were made as to the quantity of nitrogen or phosphorus
lost through deep percolation.

Carter, Bondurant, and Robbins (1971) measured nitrate and
dissolved phosphorus in surface runoff and subsurface (tile)
drainage from an 82,000 ha tract in southern Idaho.  The major
crops were alfalfa, beans, grain, sugarbeets, corn, and pas-
ture.  Precipitation averaged 21 cm per year and irrigation
supplied an additional 200 ,cm of water annually.


  Nutrient inputs in kg/ha/yr:       N            p
    Fertilizer                     60.          30.

    Irrigation water                2.3          1.0
    Precipitation               negligible   negligible
Nutrient losses in kg/ha/yr:
Surface runoff
Tile drainage
Total loss
N03-N
0. 35
35.
35.
Sol-P
0.17
0.13
0.30
   after  Carter, Bondurant,  and Robbins  (1971)

 In each  of  these  studies,  seepage  losses  of nitrogen were
 large  compared to losses by surface  runoff.   On  the other
 hand,  phosphorus  losses through  surface runoff tended  to be
 larger.   However, phosphorus losses  through seepage were
 sufficiently  large to be of significance  from a  water  quality
 standpoint.

 Erickson and  Ellis (1971)  measured the  nutrient  content  in
 drainage waters  from three experimental farms in Michigan,
 and compared  the  nutrient  losses to  the amounts  of fertilizer
 used.  Analyses  of seepage from  uncultivated, unfertilized
Nutrients added Nutrients lost
kg/ha/yr

Ferden farm
Davis farm
Muck farm
N
90
39
56
P
39
50
17
kg/ha/yr
N03-N
12
8
19
Tot-P
0.10
0.09
1.5
Lost/added
percent
N
13
20
(34)
P
0.2
0.2
(8.8)
 after Erickson and Ellis (1971)
                              22

-------
land adjacent to the Muck farm led to the conclusion that the
high values of nutrient loss were in part due to accretion
from surrounding lands, and that only a small part of the
nitrogen and phosphorus added to the Muck farm reached the
drainage water.

Losses of nitrogen as a function of fertilizer usage were
also studied by Broadbent and Chapman (1950).  They grew
vetch, clover and mustard in lysimeters at Riverside,
California.  The experiment covered a 15-year period and the
average water application (rainfall plus irrigation) was
89 cm.
                     Fertilizer  N  applied  (kg/ha/yr)

                           0         112         224


                         Nitrogen  loss  (kg/ha/yr)
Crop :
Vetch
Clover
Mustard

30
39
20

79
63
34

100
91
45
        Average  loss  for all crops
        and  treatments:    .                56

        after Broadbent and  Chapman (1950)


 Allison et al (1959)  reported the results of experiments  con-
 ducted near  Columbia, South  Carolina, in which crotalaria,
 millet, rye, cowpeas , and corn were grown in lysimeters.   The
 lysimeters were  1.2 meters deep and were filled with sandy
 soil.  Fertilization was reported to be "low."  The average
 annual rainfall  was 108 cm during the 12-year period covered
 by the study.
                              23

-------
                           Nutrient loss in kg/ha/yr
                     N03-N        Total-N        Total-P
                   Range  Mean  Range  Mean    Range

Various crops      2.4-40  24   3.6-46  29   0.09-0.17

Fallow or crops                 38-140  90
  _•_    _a _i_    * n                 OUJ-T^U^U
returned to soil
No crop :
Fertilized
No fertilizer

40
30

44
34

0.20
0.14
after Allison et al (1959)

Dreibelbis (1946) also found a correlation between nitrate
loss and fertilizer usage, but Hendrick and Welsh (1938)
reported no significant differences in nitrate loss between
fertilized and nonfertilized plots in a ten-year study con-
ducted in England.

A summary of the data giving nutrient losses from croplands
by seepage through the soil profile is given in Table  6.
Based on considerations of nutrient pathways, data from
lysimeter or subsurface drainage studies are probably most
applicable for estimating nutrient loadings of lakes which
receive irrigation return waters.  The data may also be
useful for estimating the flux of nutrients from croplands-
to groundwater aquifers, but subsequent transport to specific
lakes would be highly speculative in most instances.
SURFACE RUNOFF FROM AGRICULTURAL LANDS

A separate data grouping was prepared for nutrient losses
from agricultural lands by surface runoff.  In studies of this
type, samples of runoff water, including suspended matter, are
collected periodically from fields or experimental plots.
Runoff is not continuous, but occurs only when excessive water
is applied through irrigation or rainfall.

As was the case for seepage studies, most surface runoff in-
vestigations were conducted to evaluate alternative farming
practices, such as plowing techniques, crop rotations and
fertilizer applications, from the standpoint of minimizing
soil and nutrient losses from croplands.  Consequently,
                             24

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                   Table  6.  NUTRIENT EXPORT FROM CROPLANDS BY SEEPAGE THROUGH SOIL PROFILE
                                             N in kg/ha/yr
                                                           P  in kg/ha/yr
    Crop—study
                                       NO 3    NHi.
      Dissolved
Total inorganic Total
References
    Corn—tile drainage,  Lithuania

    Corn-oats-hay rotation—lysimeter,
      120 kg N/ha added,  New York

    Corn-oats-hay rotation—lysimeter,
      New York
                                       2.6
                                      43.
                                       2.4
                        Kinderis  (1970)
                        Bizzell  (1944)
                        Bizzell & Lyon  (1928)
tn
Corn-oats-wheat-hay rotation—
  lysimeter, New York

Corn—lysimeter, Ohio

Corn—tile drainage, Ontario
       No fertilizer
       Fertilizer added
                                           5.4 with legumes
                                           7.4 without legumes

                                           1.9
  6.1   0.20
                                                         14.
                                                                    a
        0.26
                        Dreibelbis (1946)
                                                                                Bolton et al  (1970)
                                                                                   it    ii  it    ii
    Cotton—tile drainage, 280 kg N/ha
      added, California

    Cotton—tile drainage, 220 kg N/ha
      and 36 kg P/ha added, California

    Cotton & rice—tile drainage,
      300 kg N/ha and 52 kg P/ha added,
      California

    Rice—tile drainage, 94 kg N/ha
      added, California
                                       4.11
 13.
110.
 42.
                        Meek et al (1969)
                                                                     0.05   Johnston et al  (1965)
                                                                     0.19
                                                                     0.60
                                                                                n      it   ti     it

-------
             Table  6 (continued).  NUTRIENT EXPORT FROM CROPLANDS BY SEEPAGE THROUGH SOIL PROFILE
                                             N in kg/ha/yr
                                                            P in kg/ha/yr
    Crop—study
                                                           Dissolved
                                       NOs    NHi»   Total  inorganic Total
                      References
cr>
Oats—lysimeter, England

Barley—lysimeter, England

Wheat—lysimeter, Ohio


Hay—lysimeter, England

Timothy—lysimeter, 1AO kg N/ha
  added, New York

Alfalfa—tile drainage, California

Alfalfa—tile drainage, Ontario

Alfalfa—lysimeter, Kentucky

Lespedeza—lysimeter, Kentucky

Lespedeza & rye—lysimeter,
  Kentucky

Lespedeza & bluegrass—lysimeter,
  Kentucky

Legumes—tile drainage, Lithuania

Vetch—lysimeter, California

Clover—lysimeter, California

Mustard—lysimeter, California
                                           2.5

                                           8.

                                           3.


                                           9.


                                          12.
                                          11.

                                          65.


                                          17.


                                          22.


                                           1.5
3.5

4.8   0.1
                                                          30.

                                                          39.

                                                          20.
                                                                          0.08
Hendrick & Welsh (1938)

    it        it      ti


Dreibelbis (1946)


Hendrick & Welsh (1938)


Bizzell (1944)


Johnston et al (1965)

Bolton et al (1970)

Karraker et al (1950)

    it     ii  ii    ii


    it     ii  it    it
                      Kinderis (1970)

                      Broadbent & Chapman  (1950)

-------
         Table  6 (continued).  NUTRIENT EXPORT FROM CROPLANDS BY SEEPAGE THROUGH SOIL PROFILE
                                         N in kg/ha/yr
                     P in kg/ha/yr
Crop—study
 NO 3    NHi»
                                                              Dissolved
                                                        Total inorganic Total
                        References
    Grasses—lysimeter,  New York

    Grasses—tile drainage, Lithuania

    Grasses & wheat—tile drainage,
      Lithuania

    Bluegrass sod—tile drainage,
      Ontario

    Meadow—lysimeter,  Ohio

^   Pasture—lysimeter,  England
                                       2.8

                                       0.3


                                       0.8
                                       4.3

                                       2.6
                                                      0.3   0.01
                                      Bizzell & Lyon (1928)

                                      Kinderis (1970)
                                      Bolton et al (1970)

                                      Dreibelbis (1946)

                                      Hendrick & Welsh (1938)
Various crops—tile drainage,
  Idaho

Various crops—tile drainage,
  Washington
35.


73.
                                                                0.13
100.    2.5
                        Carter et al (1971)
                                                                         7.7    Sylvester & Seabloom (1962)
Not stated—tile drainage, Illinois   18.

Not stated—tile drainage,
  Michigan, Ferden Farm
            Davis Farm
            Muck Farm
               12.
                8.
               19.
                                      Harmeson et al (1971)
                                                                         0.10   Erickson & Ellis (1971)
                                                                         0.09       "        "
                                                                         1.5

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             Table  6 (continued).  NUTRIENT EXPORT  FROM CROPLANDS  BY  SEEPAGE THROUGH SOIL PROFILE
    Crop—study
   N in kg/ha/yr     P in kg/ha/yr
                    Dissolved
 NO3    NHi,   Total inorganic Total
       References
    Fallow (no crop)—lysineter,
      South Carolina

    Fallow—lysimeter, New York

    Fallow—lysimeter, Kentucky
30.


76.

82.
0.14   Allison et al (1959)


       Bizzell & Lyon (1928)

       Karraker et al (1950)
    aTotal dissolved P
    bN09 + NOa for 8 no.
r-o
oo

-------
particulate material was intentionally included in the
samples, and particulate, along with dissolved, nutrients
were measured in most instances.  Study areas were often
quite small and usually the areas were devoted to single
crops.  Fertilization and plowing were generally uniform
within a study area, but large differences occurred amongst
study areas.

Data from surface runoff studies are given in Tables 7 and
8.   The data are grouped according to crop, but other
factors, such as slope, soil characteristics, farming prac-
tices, and antecedent soil moisture, as well as duration,
frequency and intensity of precipitation, may have a greater
influence on the quantity of nutrients lost from croplands.
Slopes (not always given) ranged from 3-20% for the studies
reported, and the annual amounts of rainfall and irrigation
water ranged from 75-220 cm.

Data from surface runoff studies may be useful for estimating
nutrient inputs from agricultural lands immediately adjacent
to lakes.  However, as shown in Table  8, by far the largest
amount of nitrogen and most of the phosphorus lost from
croplands were associated with particulate matter.  The like-
lihood that particulate matter will be transported sufficiently
far to enter a lake must be taken into account before surface
runoff data are used to estimate nutrient contributions from
croplands which exist in distant portions of a watershed.


NUTRIENT TRANSPORT BY STREAMS DRAINING AGRICULTURAL LANDS


A number of studies are reported in the literature in which
streams draining predominantly agricultural watershed were
monitored for nutrient content.  These studies typically
involved the continuous measurement of streamflow and periodic
sampling for nutrient determinations.  In many cases, sampling
frequency was related to streamflow so that additional samples
were collected during periods of high flow.  The amounts of
nutrients transported by the streams were then calculated  from
a streamflow record and a time series of nutrient concentra-
tions.  Two somewhat different approaches were used to accom-
plish this:  1) the flow hydrographs were subdivided into
segments (usually centered about the dates on which water
samples were collected), and a single nutrient  concentration
was then assumed to be characteristic of the total water mass
passing the gaging station during each time segment; 2) sample
analyses were used to develop concentration-streamflow rela-
tionships ,  and nutrient transport was computed by applying
                              29

-------
                Table  7.   NITRATE EXPORT FROM CROPLANDS BY SURFACE RUNOFF
CO
o
kg-N/ha/yr
Crop - study
Corn - Columbia, Mo.
Corn - Morris, Minn.
Cotton - Guthrie, Ok la.
Wheat - " "
Wheat - Columbia, Mo.
Oats - Morris, Minn.
Hay -
Grass sod - Guthrie, Okla.
Bluegrass sod - Columbia, Mo.
Fallow - " "
Fallow - Guthrie, Okla.
Virgin woods - " "
Burned woods - " "
Various crops - southern Idaho
Range
0.07 -0.81
0.35 -0.60


0.05 -0.99
0.11 -0.18
0.001-0.05

2.7 -6.8




Mean
1.1
0.44
0.48
0.36
1.5
0.52
0.15
0.03
0.29
4.8
0.77
0.01
0.19
0.35
Reference
Duley & Miller (1923)
Timmons et al (1968)
Daniel et al (1938)
H 11 n H
Duley & Miller (1923)
Timmons et al (1968)
n n n n
Daniel et al (1938)
Duley & Miller (1923)
n n n
Daniel et al (1938)
n * ii ii
n n n n
Carter et al (1971)

-------
                      Table  8.  NUTRIENT EXPORT FROM CROPLANDS BY SURFACE RUNOFF
Crop - study

Corn
- Geneva, New York

Corn, continuous
- Columbia, Mo.

Corn, rotation
- Columbia, Mo.

Corn, rotation
- southern Wis.
   Water only
    kg/ha/yr
Total N  Total P
 11.
negl
         Particulate only
             kg/ha/yr
         Total N  Total P
                     45.
                      6.7
                    9.1
                    2.4
  Not filtered
    kg/ha/yr
Total N Total P
                            8.9-42.
Reference
                  Bryant & Slater (1948)
                  Duley & Miller (1923)
                                                         Eck (1957)
Corn
- LaCrosse, Wis.

Corn
- Lancaster, Wis.

Corn + cover crop
- Marlboro, N.J.

Corn
- Marlboro, N.J.

Corn , cont inuous
- Morris, Minn.

Corn, rotation
- Morris, Minn.

Corn, rotation
- Coshocton, Ohio
                   1.2-3.9a 0.78-1.8a
                     12.
                     19.
                   11.
                   21.
0.4-1.2 0.06-0.08   4.1-21. 0.03-.18
1.1-1.3    0.7
         1.7-6.6 0.02-0.06
                                              Hays et al (1948)
                                         4.4     1.9     Minshall et al (1970)
                  Neal (1944)
                                              Timmons et al (1968)
                                       99-265  3.1-10.   Weidner et al (1969)

-------
                     Table  8 (continued).  NUTRIENT EXPORT FROM CROPLANDS BY SURFACE RUNOFF
GO
ro
    Crop - study

    Cotton + rice
    - California

    Cotton
    - California

    Rice
    - California

    Soybeans
    - Geneva, New York

    Tobacco
    - southern Wisconsin
    Oats,  rotation
    - southern Wisconsin

    Oats
    - LaCrosse, Wis.

    Oats,  rotation
    - Morris, Minn.


    Wheat
    - Columbia, Mo.

    Wheat, rotation
    - southern Wisconsin

    Wheat, rotation
    - Coshocton, Ohio
   Water only
    kg/ha/yr            	           	
Total N  Total P    Total N  Total P   Total N Total P   Reference
                                                 Participate only     Not filtered
                                                     kg/ha/yrkg/ha/yr
  0.22     negl
  0.75     0.01
                    3.6-58a   35-39a
5.2
                     33.
0.03
        12.
                                        3.6-59.
                                         0.9
                                                             II     If
                  11.       0.81    Johnston et al (1965)


                   6.4     0.17


                   5.2     0.11        "     "  "    "


                                   Bryant & Slater (1948)


                  37.-66.          Eck (1957)
                                                           n      n
Hays et al (1948)


Timmons et al (1968)



Duley & Miller (1923)


Eck (1957)
                                         12-35. 0.4-1.3   Weidner et  al (1969)

-------
Table  8 (continued).  NUTRIENT EXPORT FROM CROPLANDS BY SURFACE RUNOFF
    Crop -  study

    Hay, rotation
    -  southern Wisconsin

    Hay, rotation
    -  Morris, Minn.

    Alfalfa
    -  California

    Clover
    -  Geneva, New York
    Bluegrass
£   -  Geneva,  New York

    Bluegrass  sod
    -  Columbia, Mo.

    Meadow
    -  Coshocton, Ohio


    Tomatoes + cover crop
    -  Marlboro, N.J.


    Tomatoes
    -  Marlboro, N.J.

    Vegetables + cover
    crop  - Marlboro, N.J.

    Vegetables
    -  Marlboro, N.J.
          Water only        Particulate^ only     Not filtered
           kg/ha/yr             kg/ha/yrkg/ha/yr
       Total N   Total P    Total N  Total P   Total N Total P   Reference
                                               1.6-4,8
      0.45-6.5  0.07-0.39  0.0-0.03    0.0
      °-22-°*54
      0.10
negl
                              0.62     0.10
          12.      18.


          20.      29.
                                              Eck (1957)


                                              Timmons et al (1968)


                              1.6     0.20    Johnston et al (1965)


                                              Bryant & Slater (1948)
                                              Duley & Miller (1923)
                                                 negl    negl    Weidner et al (1969)
                                                                 Neal (1944)
                                               8.8-16.  7.6-14.    Knoblauch et al (1942)
                                               21.-30.  18.-30.

-------
                 Table  8 (continued).  NUTRIENT EXPORT FROM CROPLANDS BY SURFACE RUNOFF
Crop - study

Various crops
- southern Idaho

Various crops
- Washington

Apple orchard
- Coshocton, Ohio
Forest + farmland
- Tennessee Valley

Farmland
- Tennessee Valley

Row crops
- Tennessee Valley


Fallow
- Geneva, New York

Fallow
- Columbia, Mo.

Fallow
- Morris, Minn.
   Water only        Particulate only     Not filtered
    kg/ha/yr^            kg/ha/yrkg/ha/yy
Total N   Total P    Total N  Total P   Total N Total P   Reference
                        1.1-12.
             0.17
            negl
                                             1.9-3.0 0.42-0.89


                                             3.8-16. 0.78-3.7


                                             18.-36. 4.8-8.5
                  Carter et al (1971)


2.8-27. 1.0-4.4   Sylvester (1961)


  0.91    1.4     Weidner et al (1969)



                  Fippin (1945)
                                             82.-Ill  37.-53.
1.5-6.3  0.03-0.07   28.-97. 0,17-0.50
                  Bryant & Slater (1948)
                                                          Duley & Miller (1923)
                                                                                  Timmons et al (1968)
a
  Data for "cropping season" only

-------
these relationships to the stream hydrograph and integrating
over appropriate time intervals.

A summary of nutrient transport from agricultural lands by
streamflow is given in Table  9.  Flux coefficients for these
studies are less variable than  for seepage or surface runoff
studies.

                          Total-N       Total-P
                         (kg/ha/yr)    (kg/ha/yr)
               max          13.0          2.3

               min           1.2          0.03

               ave           5.1          0.38

Of the 24- values of total-phosphorus that were compiled,
only 7 were larger than 0.4 kg-P/ha/yr, and 6 of the 7 were
from the Midwest (2 from Illinois, 4 from Wisconsin).  The
largest value reported, 2.3 kg/ha/yr, was determined from a
study in Arkansas conducted by  Gearheart (1969).  In this
study, streamflow draining a 3,100 km2 watershed (80% agri-
cultural, used primarily for pasture and poultry production)
tributary to Beaver Reservoir was monitored for a seven-
month period from October through April.  Estimates of annual
values were presented by the author.  Whereas the phosphorus
value was larger, the flux of nitrogen, 3.B kg-N/ha/yr, was
less than the average for other data included in this group,
and the ratio of Tot-N/Tot-P was only 1.5—ratios for all
other studies were greater than 10.

Phosphorus transport in the Kaskaskia River watershed in
Illinois was reported by Engelbrecht and Morgan (1959, 1961).
Water samples were collected at approximately weekly intervals
at four sites and monthly at three additional locations during
the period from April-December  1956.  Some municipal effluents
were discharged to the river, but contributions from these
sources were subtracted from the total load, and values for
land drainage are presented by  the authors.  Results presented
as phosphorus loss/unit area/day were extrapolated linearly
to annual values here.

Mackenthun, Keup, and Stewart (1968) and Mackenthun  (Chairman,
1966) reported studies on the results of tributaries to Lake
Sebasticook, Maine.  The streams studied drained sparsely
populated rural areas with no significant waste discharges.
The primary crops were potatoes, apples, alfalfa, beans, and
                             35

-------
        Table   9.  NUTRIENT TRANSPORT FROM AGRICULTURAL WATERSHEDS BY STREAMS
Location - comment

Illinois,
  Kaskaskia River basin
  „ , i_          % agricul-
  Subbasin area    tural


2,
5,
6,
13,
32
320
700
100
900
500
km2
"
H
"
H
"
86.
86.
81.
76.
68.
76.
0
2
7
0
9
8
Connecticut, 85 km2 water-
  shed, 50% forested,
  "typical rural environ-
  ment"

Arkansas, 3072 km2 water-
  shed, 80% agricultural

Potomac River Basin
  (Catoctin Creek)
  280 km2, 80% farmland,
  20% forest

Ontario, tributaries of
  Bay of Quinte, 50% agri-
  cultural, 50% forests,
  many lakes and bogs
  River
  Trent
  Moira
  Salmon  )
  Napanee)
Area (km2)
  13,000
   2,700

   1,660
                                  P in kg/ha/yr
                  N in kg/ha/yr  DissolvedTot-N
                  NO3   NHi4 Total inorganic Total Tot-P References
                            11.
                  3.8
                             3.4
3.6


4.3
2.1
1.8
2.4
3.0
                                           0.03'
                                           0.05!
                                           0.85!
                                           0.44!
                                           O.llc
                                           0.10'
                          Engelbrecht &  ,
                            Morgan (1959)°
                          Harmeson et al (1971)
              0.22   15.    Frink (1967)
                                           2.3    1.5  Gearheart  (1969)
              0.27  16.    Jaworski &
                            Hetling (1970)
                          Jaworski et al  (1969)
              0.11  19.
              0.08  22.
              0.07  34.
              0.14  21.
Johnson & Owen  (1971)

-------
Table 9  (continued).  NUTRIENT TRANSPORT FROM AGRICULTURAL WATERSHEDS BY STREAMS
CO
Location - comment

North Carolina, Pigeon
  River watershed,
  350 km2

Maine, rural areas,
  sparsely populated,
  Stetson R, 74 km2

Wisconsin, average for
  36 streams, base flow
  only, 5.7-370 km2

Ontario, Grand R water-
  shed, 3500 km2

Ontario, near Toronto
     River    Area (km2)
  West number    130
     (dairy farms)
  Little Rouge    78
     (mixed farms)
  Altona
                     54
    (mixed farms)
England
  Arable land
  Permanent pasture
                                                P in kg/ha/yr
                                N in kg/ha/yr  DissolvedTot-N
                                NO3  NHi» Total inorganic Total Tot-P References
                                           1.9
                                           1.2
3.2

8.4

4.0
                                          13.
                                           8.
                                                         0.17
                                                         0.07
                          Keup  (1968)
              0.04   48.  Mackenthun et al
                             (1968)d
              0.10   12.  Minshall et al  (1969)
                          Missingham  (1967)
0.21   15.  Owen & Johnson  (1966)
            Neil, Johnson &
0.35   24.    Owen (1967)

0.17   24.
                          Owens (1970)

-------
    Table  9  (continued).   NUTRIENT TRANSPORT PROM AGRICULTURAL WATERSHEDS  BY STREAMS
CO
CO
Location - comment

Wisconsin, tributaries
to Lakes:
  Monona
  Waubesa
  Kegonsa
Prince Edward Island,
  26 km2 watershed, 28%
  potato fields, remainder
  in pasture and woodlot
Ohio, 123 ha watershed,
  25% woodlots, 50% pas-
  ture, 25% cropland
  (data for 4 con-
  secutive years)
Wisconsin,
  Menomonee R watershed
Wisconsin, 546 ha water-
  shed, dairy farming,
  0-15% slopes
                                             P in kg/ha/yr
                                            Dissolved
                                                                Tot-N
N in kg/ng/yr
     NHu Total inorganic Total Tot-P References
                                NO
                                   4.9
                                   5.5
                                   7.2
           6.7
           7.6
           9.2
                                 1.1
                                 2.2
                                 9.1
                                 1.8
                                 3.1b 1.3
           1.7
           3.1
          10.6
           4.4
0.06
0.11
0.11

0.21
0.03
0.08
0.07
0.08
0.44
0.46
17.
20.
           Sawyer (1947)
                                                                      Smith (1959)
           Taylor et al (1971)
                                                           1.6'
                                     Zanoni (1970)
           8.8
0.58
0.77  11.  Zitter (1968)
     Ortho-P + maximum inorganic condensed-P - Authors state
     that total-P values may be 20-30% higher than those reported.
    JN03 + N02
    :Total dissolved - Author states that values are within a few percent of total-P.
     Data given as loss/day or loss for part of a year—extrapolated linearly
     to an annual value.
    'Approximated from data presented.

-------
corn, which received an average of 82 kg/ha of phosphorus  as
fertilizer.  Precipitation was 102 cra/yr.  Water samples were
collected during one- to two-week periods in February, May,
July-August, and October-November.  Nutrient losses per day
were reported by the authors for each of the four sampling
periods.
                 Nutrient loads in kg/ha/day

Winter
Spring
Summer
Fall
Stetson
N
0.0029
0.0086
0.0083
0.0015
stream
P
0.0
0.00015
0.00012
0.00018
Mulligan stream
_N_ P
No flow
.00084 .00003
No flow
.0013 .00005
       after Mackenthun, Keup, and Stewart (1968)

Annual values were  computed  here by multiplying each daily
load per season by  91.25 and summing.

Phosphorus transport  from  a  3,500 km2  agricultural watershed
in Ontario (Grand River) was reported  by  Missingham  (1967).

                                Total-P
                               (kg/ha/day)

                                0.00014

                                0.00025

                                0.00021

                                0.00020

An average value  of 0.0002 kg/ha/day  converts  to  0.07  kg/ha/yr
which  is, most  likely, an  underestimate  of the amount  of phos-
phorus transported  annually  from  the  basin.

Minshall, Nichols,  and Witzel (1969)  carried out  a  two-year
study  to  determine  the amount of  nutrients in base  flow^of
southwestern Wisconsin streams.   Flow rates  were  determined
for  36 streams  with drainage areas  varying from 570  to
37,000 ha.   Samples were collected,  and  flows were  measured
at times  when no surface runoff was  entering the  streams.

The  area studied was 90% agricultural, with 40% in  contour
strip-cropped farmland (corn, oats  and alfalfa),  40% in
                              39

-------
pasture, and 10% woodland.  Livestock enterprises were preva-
lent.  Soils were moderately- and well-drained silt loams,  and
the mean annual precipitation for the area was 83 cm.   An
average of 9 kg/ha/yr of nitrogen was applied as manure or
artificial fertilizers.
                  Nutrient loss in kg/ha/yr
                             1966            1967

High
Low
Weighted ave
Tot-N
4.2
0.4
1.1
Tot-P
0.25
0.01
0.08
Tot-N
5.5
0.5
1.4
Tot-P
0.49
0.03
0.12
        after Minshall, Nichols, and Witzel (1969)

Zanoni  (1970) conducted a study of the Menomonee River basin in
southeastern Wisconsin, and reported that an average of 1.18 kg/
ha of total soluble phosphorus was contributed annually to
Lake Michigan from land drainage in the watershed.  The total
watershed contains 350 km2 of which 38% is agricultural, 43%
is urban, and the remaining 19% is woodlots, parks and unpro-
ductive land.  An analysis of runoff from sub-basins in the
watershed showed that urban areas contributed 0.58 kg/ha/yr.
Drainage from the remainder of the watershed, primarily rural
lands,  can be computed to yield a contribution of 1.6 kg/ha/yr.


MANURE HANDLING


Manure handling problems, particularly those associated with the
dairy industry in the northern portions of the country, in many
instances are met by spreading of manure on frozen, snow-covered
fields for several months of the year.  The impervious fields,
coupled with rapid runoff during spring thaws, greatly increase
the possibility for nutrient losses as a result of this prac-
tice.

Nutrient characteristics of manure from domestic farm animals
are given in Table 10 (based on Porcella et al, 1974).  A dairy
cow weighs about 450 kg, so on an annual basis the manure
from a single cow would contain on the order of 38 kg of
nitrogen and 25 kg of phosphorus.  If it is assumed that
                             40

-------
        Table 10.
NUTRIENT CHARACTERISTICS OF MANURE
FROM DOMESTIC ANIMALS^













Poultry
Ducks
Swine
Dairy cattle
Beef cattle
.Sheep
tit , kg/animal
bO
•H
cu


*0>
bO
ifl

QJ

^
2
2
125
450
450
50
fcT
•o
bO
\
bO

n
0)
3
c
i
it)
•a
•v^
bO
~^,
bO

«»
10
0
OJ
.60
.60-1.6
.42
.34
.18
.25
imal/yr
c
nJ
~--v
bO
•^
r.
*tzt
1
,H
nJ
-H
O
0.5
5.8
23.
38.
53.
11.
-P/animal/yr
bO
y

t*
en
fc
o
,111
cu
en
O
£
0.2
0.2-0.5
8.
25.
13.
2.
aBased on average values presented by Porcella et al (1974).


50 cows are maintained on a 100-ha farm, that for 4 months of
the year the manure from these cows' is spread on frozen fields,
and that 10% of the nutrients are carried in runoff waters,
then about 63 kg-N and 42 kg-P would be lost.  Viewing this as
an annual loss distributed over the entire farm, this amounts
to nutrient export rates of 0.6 kg-N/ha/yr and 0.4 kg-P/ha/yr.
Comparing these values with those given in Table  9  shows that
manure handling could result in a very significant loss of
phosphorus from agricultural lands.

A study conducted in Vermont (Midgely and Dunklee, 1945) showed
that from 4.5-13 kg-N/ha was carried in runoff waters from
fields which received winter application of manure at a rate
                              41

-------
of about 1800 kg/ha (10 tons/acre).   Nitrogen loss was reported
to depend primarily on the amount of volatilization which
occurred prior to runoff,  and the effect of slope was minimal
because of the impervious  nature of the soil.  Nitrogen losses
ranged from 3.3-11,5%; phosphorus losses were similar, ranging
from 4.8-10%.

Minshall et al (1970)  conducted studies in southwestern
Wisconsin and concluded that up to 20% of the nitrogen and 13%
of the phosphorus contained in manure applied in winter on
frozen ground may be lost  under conditions favoring maximum
early spring runoff.  In one instance, a 1.5 cm rain in January
caused losses of nitrogen  and phosphorus amounting to 17% and
6% respectively, which corresponded to about 15 kg-N/ha and
1.9 kg-P/ha.  These investigators also found that summer appli-
cations of manure incorporated into the soil resulted in less
nutrient runoff than plots receiving no manure.
REFERENCES
Allison, F.  E. ,  E.  M.  Roller,  and J.  E. Adams.  1959.  Soil
     Fertility  Studies in Lysimeters  Containing Lakeland Sand.
     Tech.  Bull.  1199, U.S.  Dept. of  Agriculture, Washington,
     D.C.  p. 1-62.

Bizzell, J.  A.   1944.   Lysimeter Experiments, VI. The Effects
     of Cropping and Fertilization on the Losses of Nitrogen
     from the Soil.   Mem. 256, Agr. Exp. Sta., Cornell Univ.,
     Ithaca, N.Y.   p.  1-14.

Bizzell, J.  A.,  and T. L. Lyon.  1928.  Composition of
     Drainage Waters from Lysimeters  at Cornell University.
     Proc.  First International Cong.  Soil Sci. Com. _2: 342-349.

Bolton, E.  F.,  J. W. Aylesworth, and  F. R. Hore.  1970.
     Nutrient Losses through Tile Lines under Three Cropping
     Systems and Two Fertility Levels on a Brookston Clay Soil,
     Can. J. Soil Sci. 50:275-279.

Broadbent,  F. E. ,  and H.  D.  Chapman.   1950.  A Lysimeter Inves-
     tigation of Gains, Losses and Balance of Salts and Plant
     Nutrients  in an Irrigated Soil.   Soil Sci. Soc. Amer.
     Proc.  14:261-269.

Bryant, J.  C.,  and  C.  S.  Slater.  1948.  Runoff Water as an
     Agent in the Loss of Soluble Materials from Certain Soils
     Iowa State Coll.  J.  Sci.  22:269-312.
                             42

-------
Carter, D.  L., J. A. Bondurant, and C.  W.  Robbins.   1971.
     Water Soluble N03-N, PO^-P, and Total Salt Balances on
     a Large Irrigation Tract,  Soil Sci.  Soc.  Amer.  Proc.
     35:331-335.

Daniel, H.  A., H. M. Elwell, and H. J.  Harper.   1938.  Nitrate-
     Nitrogen Content of Rain and Runoff Water from Plots  under
     Different Cropping Systems on Vermon Fine Sandy Loam.
     Soil Sci. Soc. Amer. Proc. _3:230-233.

Dreibelbis, F. R.  1946.  Some Plant Nutrient Losses in Gravi-
     tational Water from Monolith Lysimeters at Coshocton,
     Ohio.  Soil Sci. Soc. Amer. Proc.  11:182-188.

Duley, F. L., and M. F. Miller.  1923.   Erosion and Surface
     Runoff under Different Soil Conditions.  Res.  Bull.  63,
     Missouri Agr. Exp. Sta.   50 p.

Eck, P.  1957.   Fertility Erosion Selectiveness on Three
     Wisconsin Soils.  Ph.D. Thesis, Univ. of Wisconsin,
     Madison, Wis.

Engelbrecht, R.  S. , and J. J.  Morgan.  1961.  Land Drainage as
     a Source of Phosphorus in Illinois Surface Waters.  Tech.
     Rep. W61-3, Trans.  1960  Seminar on Algae and Metropolitan
     Wastes, Robert A. Taft San. Engr. Ctr., Cincinnati, Ohio.
     p.  74-79.

Engelbrecht, R.  S., and  J. J.  Morgan.  1959.  Studies on the
     Occurrence  and Degradation of Condensed Phosphate in
     Surface Waters.   Sewage  Indus. Wastes  31:458-478.

Erickson, A. E., and B.  G.  Ellis.   1971.  The Nutrient Content
     of  Drainage Water from Agricultural  Land.  Res. Bull.  31,
     Agr. Exp.  Sta., Michigan State Univ.,  East Lansing, Mich.
     16  p.

Fippin,  E.  0.   1945.   Plant Nutrient Losses  in  Silt  and Water
     in the Tennessee  River System. Soil Sci.  60:223-239.

Frink,  C.  R.   1967. Nutrient Budget:  Rational Analysis_of
     Eutrophication in a Connecticut Lake.   Environ. Sci.
     Technol.  K5):425-428.

Gearheart,  R.  A.  1969.   Agricultural  Contribution to  the
     Eutrophication Process in Beaver  Reservoir.   Presented
      at Dec.  9-12, 1969 Meeting of Amer.  Soc.  Agr.  Engrs.,
      Chicago,  111.  19 p.
                              43

-------
Harmeson, R. H., F. W. Sollo, Jr., and T. E. Larson.  1971.
     The Nitrate Situation in Illinois.  J. Amer. Water Works
     Assoc. 63(5):303-310.

Hays, 0. E. , C. E. Bay, and H. H. Hull.  194-8.  Increasing
     Production on an Eroded Loess-Derived Soil.  J. Amer. Soc.
     Agron. 4-0:1061-1069.

Hendrick, J., and H. D. Welsh.  1938.  Further Results from
     the Craibstone Drain Gauges.  Trans. Royal Highland Agr.
     Soc.,  Scotland 50:184-202.

Holt, R. F., D. R. Timmons, and J. L. Latterell.  1970.
     Accumulation of Phosphate in Water.  J. Agr. Food Chem.
     181: 781-784.

Jaworski, N. A., and L. J. Hetling.  1970.  Relative Contri-
     butions of Nutrients to the Potomac River Basin from
     Various Sources.  Tech. Rep. 31, Middle Atlantic Region,
     Fed. Water Pollut. Con. Adm.  36 p.

Jaworski, N. A., 0. Villa, Jr., and L. J. Hetling.  1969.
     Nutrients in the Potomac River Basin.  Tech. Rep. 9,
     Middle Atlantic Region, Fed. Water Pollut. Con. Adm.
     40 p.

Johnson, M. G., and G. E. Owen.  1971.  Nutrients and Nutrient
     Budgets in the Bay of Quinte, Lake Ontario.  J. Water
     Pollut. Con. Fed. 43(5);836-853.

Johnston, W. R., F. Ittihadieh, R. M. Daum, and A. F. Pillsbury,
     1965.  Nitrogen and Phosphorus in Tile Drainage Effluent.
     Soil Sci. Soc. Amer. Proc. 29:287-289.

Karraker, P. E., C. E. Bortner, and E. N. Fergus.  1950.
     Nitrogen Balance in Lysimeters as Affected by Growing
     Kentucky Bluegrass and Certain Legumes Separately and
     Together.  Bull. 557, Kentucky Agr. Exp. Sta.  p. 1-16.

Keup, L. E.  1968.  Phosphorus in Flowing Waters.  Pergamon
     Press, Oxford, England.  Water Res. 2_: 373-386.

Kilmer, V.  J., J. W. Gilliam, R. T. Joyce,  and J. F. Lutz.
     1971.  Loss of Fertilizer Nutrients from Soils to Drainage
     Waters. Part I. Studies of Grassed Watersheds in Western
     North  Carolina.  Rep. 55, Water Resources Res. Inst.,
     Univ.  of North Carolina, Raleigh, N.C.
                              44

-------
Kinderis, Z. B.  1970.  Leaching of Nutrients by Drainage
     Waters.  Soviet Soil Sci. !_: 99-108.

Knoblauch, H. C.s L. Kolodny, and G. D. Brill.  1942.   Erosion
     Losses of Major Plant Nutrients and Organic Matter from
     Collington Sandy Loam.  Soil Sci. 53:369-378.
Mackenthun, K. M.  (chrm.).  1966.  Fertilization and Algae in
     Lake Sebasticook, Maine.  Robert A. Taft San. Engr.  Ctr.,
     Cincinnati, Ohio.  124 p.

Mackenthun, K. M., L. E. Keup, and .R. K. Stewart.  1968.
     Nutrients and Algae in Lake Sebasticook, Maine.  J.  Water
     Pollut. Con. Fed. 40(2):Part 2:R72-R81.

Meek, B. D. , L. B. Grass, and A. J. MacKenzie.  1969.  Applied
     Nitrogen Losses in Relation to Oxygen Status of Soils.
     Soil Sci. Soc. Amer. Proc. 33:575-578.

Midgely, A. R., and Dunklee, D. E.  1945.  Fertility Runoff
     Losses from Manure Spread during the Winter.  Bull.  523,
     Vermont Agr. Exp. Sta.

Minshall, N. E., M. S. Nichols, and S. A. Witzel.  1969.   Plant
     Nutrients in Base Flow  of Streams in Southwestern
     Wisconsin.  Water Resources Res. _5_( 3) : 706-713 .

Minshall, N. E., S. A. Witzel, and M. S. Nichols.  1970.
     Stream Enrichment from  Farm Operations.  J.  San. Engr.
     Div., Amer. Soc. Chem.  Engineers 96CSA2):513-524.

Missingham, G. A.  1967.  Occurrence of  Phosphates in Surface
     Waters and Some Related Problems.   J. Amer.  Water Works
     Assoc. 59:187-211.

Neal, 0. R.  1944.  Removal  of Nutrients from the Soil by Crops
     and Erosion.  J. Amer.  Soc. Agron.  36:601-607.

Neil, J. H., M. G. Johnson,  and G. E. Owen.   1967.   Yields and
     Sources of Nitrogen from Several Lake Ontario Watersheds.
     In: Proc. Tenth Conference on Great Lakes  Research,
     Michigan  Univ., Ann Arbor, Mich.  p.  375-381.

Owen, G. E., and M. G. Johnson.   1966.   Significance of Some
     Factors Affecting Yields of Phosphorus  from Several Lake
     Ontario Watersheds.  Pub.  15, Great Lakes  Res.  Div.,
     Univ.  of  Michigan, Ann  Arbor, Mich.  p.  400-410.
                              45

-------
 Owens, M.   1970.   Nutrient Balances  in Rivers.   J.  Soc.  Water
      Treat,  and Exam.  3.9_( 3): 239-252.

 Porcella,  D.  B.,  A.  B.  Bishop,  J.  C.  Andersen,  0. W.  Asplund,
      A.  B.  Crawford, W.  J.  Grenney,  D.  I.  Jenkins,  J.  J.
      Jurinak, W.  D.  Lewis,  E. J. Middlebrooks,  and  R.  M.
      Walkingshaw.  1974.   Comprehensive Management  of Phos-
      phorus  Water Pollution.  Rep. EPA-600/5-74-010 ,  U.S.
      Environmental Protection Agency,  Washington, D.C.   411  p.

 Sawyer,  C.  N.  1947.  Fertilization  of Lakes by Agricultural
      and Urban Drainage.   New England Water Works Assoc. J.
      6K2):  109-127.

 Smith, M.  W.   1959.  Phosphorus Enrichment of Drainage Waters
      from Farm Lands.  J.  Fish. Res.  Bd. Can. 16:887-895.

 Sylvester,  R. 0.   1961.  Nutrient Content of Drainage Water
      from Forested,  Urban  and Agricultural Areas.   Tech. Rep.
      W61-3,  Trans.  1960  Seminar on Algae and Metropolitan
      Wastes,  Robert  A. Taft San. Engr.  Ctr., Cincinnati, Ohio.
      p.  80-87.

 Sylvester,  R. 0., and R. W. Seabloom.   1962.  A Study on the
      Character and Significance of Irrigation Return Flows in
      the Yakima River Basin.  Univ.  of  Washington,  Seattle,
      Wash.   104 p.

 Taylor,  A. W.,  W. M. Edwards, and E.  C. Simpson.  1971.
      Nutrients  in Streams  Draining Woodland and Farmland near
      Coshocton, Ohio.  Water Resources  Res. 7(l):81-89.

 Timmons, D. R., R. E. Burwell, and R.  F. Holt. '  1968. 'Loss
      of  Crop  Nutrients through Runoff.  Minn. Sci.  24(4):16-18.

Webber,  L. R.,  and D. E. Elrick.  1967.  The Soil and Lake
      Eutrophication.  Proc. Tenth Conference on  Great Lakes
      Research,  Michigan Univ., Ann Arbor, Mich.  p. 404-409.

Weidner, R. B., A. G. Christiansen, S.  R. Weibel, and G. G.
      Robeck.  1969.  Rural Runoff as a  Factor in Stream
      Pollution.   J. Water Pollut. Con.  Fed. 36(7):914-924.

Zanoni, A. E.   1970.  Eutrophic Evaluation of a  Small Multi-
      Land Use Watershed.  Tech. Completion Rep., Water Resources
      Center,  Univ. of Wisconsin, Madison, Wis.
                              46

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Zitter, B. A.  1968.  Quantifying Amounts of Nutrients  from
     an Agricultural Watershed.  M.S.  Thesis, Agr.  Engineering,
     Univ. of Wisconsin, Madison, Wis.  215 p.

Zwerman, P. J., et al.  1971.  Management of Nutrients  on
     Agricultural Land for Improved Water Quality.   Rep.
     13020 DPB 08/71, U.S. Environmental Protection Agency,
     Washington, D.C.  151 p.

-------
              NUTRIENT EXPORT FROM URBAN AREAS
The hydrology of  urban areas contributes to the rapid trans-
port of dissolved and suspended materials from cities to
nearby receiving  waters and increases the potential for
nutrient transport.  Two factors are particularly important:
1) the large amount  of impermeable areas brought about by
urban development and 2) storm sewer systems.  Storm sewers
provide a relatively direct pathway from virtually all parts
of a city to the  receiving waters; short distances of over-
land flow are sufficient to transport nutrients from remote
portions of an  urban watershed.  The impermeable areas
prevent infiltration and increase the intensity of surface
runoff.  Consequently, considerable amounts of soil and
other particulate matter are eroded and transported through
the storm sewer system.  These characteristics, particularly
the intermittent  high flows, make it difficult to apply con-
ventional methods of wastewater treatment to storm water
runoff and increase  the need for alternate management tech-
niques.

A number of studies  are reported in the literature in which
the export of materials in urban runoff have been quantified.
However, many of  the earlier studies were conducted in areas
served by combined sanitary-storm sewer systems, and it is
virtually impossible to separate the component appearing in
stormwater outlets due to overloading of sanitary sewers ,
from that due to  urban surface runoff (Weibel, 1969).  Five
studies, however, have been conducted recently with the
objective of determining the quality of urban surface runoff.
In addition, data were compiled for three locations in which
streams with predominantly urban watersheds were monitored
for nutrient content.  A summary of these data is given in
Table 11.

The most extensive study of urban runoff was conducted in
Tulsa, Oklahoma (Avco Corp., 1970).  Drainage from 15 test
areas was sampled and analyzed for Kjeldahl nitrogen and
dissolved inorganic  phosphorus.  The largest annual phosphorus
export, 2.9 kg/ha/yr, was from a light industrial area which
was still under development.  Export from all other areas fell
within the range  of  0.5-1.2 kg P/ha/yr.  Nitrogen export ranged
                             1*8

-------
                 Table 11.  EXPORT OF NUTRIENTS FROM URBAN AREAS
Study area
Surface runoff studies:

  Tulsa, Oklahoma

  Durham, North Carolina,
  433 ha, 37% impermeable

  Ann Arbor, Michigan,
  1540 ha

  Madison, Wisconsin,
  50 ha, residential

  Cincinnati, Ohio,
  11 ha, 37% impermeable

Drainage area studies:
  Rock Creek basin
  (Potomac), 20,000 ha,
  60% urban, 10% forest,
  30% farmland

  Milwaukee, Wisconsin,
  3160 ha, 98% urban,
  50% residential

  England, urban areas
    kg-N/ha/yr        kg-P/ha/yr
                   Dissolved
  N03   NHt> Total  inorganic Total References
             2.1a
(0.9)  (0.8)  (2.1)
 0.67   .50  5.0
 «-   2.8   •*•  8.8
     1.8
2. 3
             4,
         0.9b




        (1.0)


         0.64
0.02
                      0.571
             Avco Corp.  (1970)

        1.2  Bryan (1970)

             Burm et alc
       (3.1)
        1.1
(1968)

Kluesener S Lee
(1974)

Weibel (1969)
Jaworski £
Hetling (1970)
                      Zanoni (1970)
                      Owens  (1970)
 organic N
^total disssolved-P
GData given are for three months, June, July, August, only.

-------
 from 0.9-4.0 kg/ha/yr and averaged  2.2 kg/ha/yr.   Population
 densities averaged 15 persons/ha.

 One of the first studies of urban runoff was  conducted by
 Weibel et al (1964) in an 11-ha residential and light com-
 mercial area in Cincinnati, Ohio.   Resident population
 density was 25 persons/ha.   Burm et al (1968) conducted a
 similar study in Ann Arbor, Michigan;  however, the  flux of
 N and P was reported for only  the months of June, July and
 August.  A comparison of these data with others in  Table 11
 suggests that export from the  Ann Arbor area  is considerably
 higher than that reported for  other cities.

 Kluesener (1972) measured nutrient  export  from a residential
 watershed in Madison, Wisconsin and suggested that  phosphorus
 leaching from leaves may be an important component  of urban
 runoff.  This is supported to  some  extent by  the Tulsa study
 (Avco Corp., 1970) where phosphorus export appeared to be
 related to the density of tree cover.

 Jaworski and Hetling (1970) studied nutrient  runoff in the
 Potomac basin and reported results  for the Rock Creek basin
 which is approximately 60%  urban.   They found that  1.8 kg/ha/
 yr of nitrate-N, 2.3 kg/ha/yr  of total-N, and 0.02  kg/ha/yr
 dissolved inorganic-P were transported from the basin.  These
 data are not directly comparable to those listed in the upper
 portion of Table 11, because this study was conducted by moni-
 toring continuously flowing streams, whereas the other data
 are for runoff from storm sewers.

 Another drainage area study was  conducted by Zanoni (1970)
 in which nutrient transport from the Menomonee River basin
 in southeastern Wisconsin was  measured.  It was reported
 that the annual loss of total  soluble  phosphorus from a
 densely populated urban sub-basin (3160 ha) amounted to
 0.57 kg P/ha/yr.   All samples  were  analyzed for total soluble
 phosphorus  but,  periodically,  analyses  were conducted for
 dissolved inorganic and total  phosphorus as well.    Based on
 these  results,  the author reported  that, on the average,
 dissolved inorganic phosphorus amounted to 70-80% of total
 soluble,  and there was very little  difference between total
 soluble and total phosphorus.

 Owens  (1970)  calculated the nutrient loss from urban areas
 to  several  rivers  in England by  subtracting sewage  contri-
butions  from the  total load carried by  the streams.
                             50

-------
Table 12 lists the average nutrient concentration reported
for urban runoff.  Data for two additional cities, Seattle,
Washington (Sylvester, 1961) and Washington, B.C. (DeFilippi
and Shin, 1971), are also given.


FACTORS CONTRIBUTING TO THE NUTRIENT CONTENT OF URBAN RUNOFF

Several factors have been identified as being potentially
significant contributors of nutrients in urban runoff; how-
ever, for the most part, studies to document their importance
have not been conducted.

1.  urban erosion - Sediment transport, often associated
with the construction industry, is often thought to be a key
factor.  A study of land drainage in metropolitan Detroit by
Thompson (1970) indicated that the erosion from areas under
urban development contributed 155 metric tons of sediment
per hectare per year compared with an overall average erosion
rate of about 7 metric tons per hectare per year for the
metropolitan area and an overall average erosion rate of
6 metric tons per hectare per year for southeast Michigan.
Thus, it was concluded that road construction and urban
development would account for significant amounts of sedi-
ment even though the total  acreage under construction may be
relatively low.

2.   lawn fertilisers - Use  of home fertilizers to maintain
luxuriant lawns  and gardens is  a common practice in urban
areas, particularly in newer residential subdivisions.  In-
creased use of  fertilizers  is likely in future years.  One
management approach might be to encourage the use of fer-
tilizers which  contain little or no phosphorus because, in
many situations, lawns require  supplemental nitrogen but
there is no need for additional phosphorus.

3.   animal populations - Surprisingly  large populations of
cats and dogs are maintained in many urban  areas.  Pets
could contribute relatively large  amounts of nutrients to
small areas.

H.   leaohate from  leaves -  Cowen and Lee  (undated) reported
on the results  of  leaching  experiments in which  phosphorus
was  removed from leaves by  soaking them in water.  They con-
cluded that leaves  could contribute significant  amounts of
phosphorus to urban runoff, and advocated  leaf pickup  and
removal and advised against burning and storing  leaves in
gutters.
                              51

-------
             Table 12.  AVERAGE NUTRIENT  CONCENTRATIONS  IN URBAN  RUNOFF
Cn
Study area
Tulsa, Okla
Durham, N.C.
Ann Arbor,
Mich
Washington,
B.C.
Madison, Wis
Seattle, Wash
Cincinnati ,
Ohio
mg-N/1 mg-P/1
Dissolved
NO 3 NHi^ Organic Total inorganic Total
0.85 0.37
0.19
1.5 1.0 1.0 3.5 0.8a 5,0
2.1 1.3
0.60 O.H5 3.5 if. 5 0.57 0.98
0.5 2.0 2.5 0.08 0.21
•*• 1.0 •* 3.1 0.36a
References
Avco Corp (1970)
Bryan (1970)
Burm et al (1968)
DeFilippi 8 Shih
(1971)
Kluesener 8 Lee
(1974)
Sylvester (1961)
Weibel et al
(1969)
      Total dissolved-P

-------
5.  gasoline additives - It is estimated that 2.5 million
pounds of phosphorus are consumed each year as additives in
gasolines burned in motor vehicles in this country.  Concen-
trations in gasoline may be as high as 12.6 mg P/l (Bartsch,
1972).  However, even if it is assumed that one-half of all
gasoline is consumed in urban areas, and all of the phosphorus
consumed reaches surface waters, this would amount to only
0.2-2% of the estimated phosphorus contribution from urban
runoff.

6.  de-icing compounds - Some de-icing compounds used in
northern cities contain phosphorus, but an analysis by
Struzeski (1971) indicates that this contribution is insig-
nificant in most situations.
REFERENCES
AVCO Economic Systems Corporation.  1970.  Storm Water Pollu-
     tion from Urban Land Activity.  Rep. 11034 FKL 07/70,
     Federal Water Qual. Adm., U.S. Dept. of the Interior,
     Washington, B.C.   325 p.

Bartsch, A. F.  1972.   Role of Phosphorus in Eutrophication.
     Rep. EPA-R3-72-001, Environmental Protection Agency,
     Washington, D.C.

Bryan, E. H.  1970.  Quality  of Stormwater Drainage from
     Urban Land Areas in North Carolina.  Rep. 37, Water
     Resources Research Inst., Univ. of North Carolina,
     Chapel Hill, N.C.  4M- p. plus append.

Burm, R. J., D. F. Krawczyk,  and G. L. Harlow.  1968.
     Chemical and Physical Comparison of Combined and
     Separate Sewer Discharges.  J. Water Pollut. Con. Fed.
     4£: 112-126.

Cowen, W., and G. F. Lee.  Undated.  Leaves as a Source of
     Phosphorus.  Water Chemistry Prog., Univ. of Wisconsin,
     Madison, Wis.

DeFilippi, J. A., and C. S. Shih.  1971.  Characteristics
     of Separated Storm and Combined Sewer Flows.  J. Water
     Pollut. Con. Fed.  4_3( 10) : 2033-205 8.

Jaworski, N. A., and L. J. Hetling.  1970.  Relative Contri-
     butions of Nutrients to  the Potomac River Basin from
     Various Sources.   Tech.  Rep. 31, Middle Atlantic Region,
     Federal Water Pollut. Con. Adm.  36 p.
                             53

-------
Kluesener, J. W.  1972.  Nutrient Transport and Transforma-
     tion in Lake Wingra, Wisconsin.  Ph.D. Thesis, Water
     Chemistry Dept., Univ. of Wisconsin, Madison, Wis.

Kluesener, J. W.s and G. F. Lee.  1974.  Nutrient Loading
     from a Separate Storm Sewer in Madison, Wisconsin.
     J. Water Pollut. Con. Fed. 4jj_:920-936.

Owens, M.  1970.  Nutrient Balances in Rivers.  J. Soc. Water
     Treat, and Exam. 19_( 3) : 239-252.

Struzeski, E.  1971.  Environmental Impact of Deicing.
     Rep. WPCRS 11040 6KK 06/71, Environmental Protection
     Agency, Washington, B.C.

Sylvester, R. 0.  1961.  Nutrient Content of Drainage Water
     from Forested, Urban and Agricultural Areas.  Tech.
     Rep. W61-3, Trans.  1960 Seminar on Algae and Metropolitan
     Wastes, Robert A. Taft San. Engr. Ctr. , Cincinnati, Ohio.
     p.  80-87.

Thompson, J. R.  1970.   Soil Erosion in the Detroit Metro-
     politan Area.  J. Soil and Water Conservation 25_(1) : 8-10 .

Weibel,  S. R.   1969.  Urban Drainage as a Factor in Eutrophi-
     cation.  In: Eutrophication: Causes, Consequences,
     Correctives.  National Academy of Science, Washington,
     D.C.  p. 383-403.

Weibel,  S. R. ,  R. J. Anderson, and R. L. Woodward.  1964.
     Urban Land Runoff as a Factor in Stream Pollution.  J.
     Water Pollut. Con.  Fed. 3
 Zanoni,  A.  E.   1970.   Eutrophic Evaluation of a Small Multi-
      Land Use  Watershed.   Tech. Completion Rep. OWRR A-014-
      Wis.,  Water Resources Center, Univ. of Wisconsin, Madison,
      Wis.
                              54

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                NUTRIENT EXPORT FROM FORESTS
Forested lands are known to have relatively high absorptive
capacities with minimal amounts of surface runoff and accom-
panying soil erosion.  Consequently, most studies of nutrient
export from forested lands are conducted by monitoring stream-
flows or measuring vertical nutrient movement through the
soil profile in forested areas.  The only surface runoff
study identified was conducted by Daniel, Elwell and Harper
(1938).  They analyzed surface runoff from plots of virgin
woods in Oklahoma and found that nitrogen runoff as nitrate-N
amounted to 0.01 kg/ha/yr.

Cole and Gessel (1965) placed tension lysimeters beneath
the floor (2.5 cm depth) and the rooting zone (90 cm depth)
of four 0.04-ha Douglas fir forest areas near Seattle,
Washington.  The soil was composed of 50 to 80% gravel.  Two
of the plots received added nitrogen at the rate of 224 kg/ha.
Leachates were collected and analyzed monthly.
                               Nutrient loss  (kg/ha/yr)
                               Total N         Total P
                                  Rooting         Rooting
    Treatment               Floor   zone    Floor   zone
Untreated
Clear-cut
Urea fertilizer
Ammonium fertilizer
3.9
11
173
200
0.54
0.97
0.69
1.1
0. 84
2.3
5.5
4.5
0.03
0.11
0.08
0.17
    after Cole and Gessel (1965)

Several studies have been conducted in which  streams flowing
from forested watersheds were monitored for nitrogen and
phosphorus.  Cooper (1969) presented data showing the quanti-
ties of nitrogen and phosphorus removed from  forested areas
in northern Minnesota.  The  data were determined from the
weighted average of weekly samples collected  from August to
November.  The forests were  predominantly aspen-birch and lay
in an area of poor drainage.
                              55

-------
           Nutrient Export in g/ha/day (4 months)
Watershed
area (ha)
2,150
2,850
958
13,000
Mean
NHi,-N
0.43
0.50
0.31
0.43
0.42
N03-N
7.3
6.0
0.7
3.2
4.3
Organic
N
5.9
5.7
2.6
5.5
4.9
Total
P
0.30
0.50
0.23
0.37
0.35
         after Cooper (1969)

Sylvester  (1961) measured the nutrient content in streams
emerging from three forested areas of the Yakima River basin
in Washington.  The watersheds contained large reservoirs,
roads and  some logging but no significant human habitation.
The drainage areas were 47,000,  62,000, and 32,000 ha for
the Yakima, Tieton, and Cedar River basins respectively.
                 Nutrient Export (kg/ha/yr)

Yakima
Tieton
Cedar
Mean
NO 3
2.37
0.95
1.06
1.46
TKN
0.95
0.51
-
0.73
Tot-N
3.32
1.46
-
2.39
Sol-P
0.08
0.05
0.07
0.07
Tot-P
0.83
0.86
0.36
0.68
         after Sylvester (1961)

Viro (1953) studied the nutrient loads carried by the five
largest river systems in Finland, representing, in general,
forest areas with granite bedrock.  The total drainage area
was 34 million ha, and precipitation within the drainage area
varied from 45-69 cm.  River water samples were taken monthly
and analyzed for Kjeldahl nitrogen and total phosphorus.
                             56

-------
River
Vuoksi
Kymi joki
Kokemaen j oki
Oulujoki
Kemi joki
Mean
Area
(ha)
6.1
4.9
8.4
4.7
9.5

M
M
M
M
M

Nutrient loads
(kg/ha/yr)
TKN
2.2
1.
1.
2.
1.
(1.
6
8
1
7
9)
0
0
0
0
0
(0
p
.29
.26
.29
.32
.18
.26)
         after Viro (1953)


Bormann et al (1968) studied the effects of clear-cutting and
herbicide treatment on a small forested watershed in New
Hampshire.  Nutrient losses for the treated (15.6 ha) and un-
disturbed (13.2 ha) areas were determined by weekly sampling
and flow rate measurements of streams draining the areas.
Analysis was made for ammonia and nitrate nitrogen.  Annual
precipitation was 125 cm.  They noted little difference in the
annual flux of ammonia nitrogen from the two areas, but trans-
port of nitrate was much greater from the clear-cut area.
NHi+-N
N03-N
Nutrient loads
Undisturbed
0.5-0.6 (0.55)
1.0-1.5 (1.3)
(kg/ha/yr)
Clear-cut
0.4-1.2 (0.8)
1.3-58. (30.)
         after Bormann et al (1968;


A summary of data describing the transport of nutrients from
forested areas as determined by drainage area studies is given
in Table 13.

Export of total nitrogen averaged 2.9 kg N/ha/yr and ranged
from 1.3 to 5.1 kg N/ha/yr.  Total phosphorus flux ranged
from 0.01 to 0.86 kg P/ha/yr with an average value of 0.27 kg
P/ha/yr.
                             57

-------
             Table 13.  NUTRIENT EXPORT FROM FORESTED WATERSHED VIA STREAMFLOW
en
oo


Study area
Forested watershed,
New Hampshire
Woodlands , marsh , open
fields , Ohio
Four aspen + birch
watersheds in
northern Minnesota
88% fores-ted watershed
in the
Potomac River basin
Three forested areas
in Washington
Woodlands in Ohio,
one watershed, data
for three years

Five large forested
river basins in
Finland

Forested watershed
in Sweden
N

N03

1. 3


2.7
2.2
0. 3
1.2

"«-
2.4
1.0
1.1
0. 8
1.6
0.7







in kg/ha/yr

NH., Total

0. 6


0.16 5.1
0.18 4.5
0.11 1.3
0.16 3.4

1.3 -»• 1.6
3.3
1.5
1.4
3.2
2.8
2.2°
1.6C
1.8C
2. 1C
1.7°


P in kg/ha/yr
Dissolved
inorganic







0.08
0.05
0.07
0.04b
0.0 7b
0.0 3b





n n?
\S 9 \J *-,

Total

0 .02
OC 1
. b /
0.11
0.18
0,08
0.14

0.01
0.83
0.86
0.36

0.29
0.26
0.29
0.32
0.18
n n R
U * \j U

References
Bormann et al
(1968)
Cooke et al
(1973)
Coopera (1969)
Jaworski &
Hetling (1970)
Sylvester (1961)
Taylor et al
(1971)


Viro (1953)


Brink &
Gustafson (1970)
     aData given for 4 months, extrapolated to  12 months.

     bTotal soluble P
     CTotal Kjeldahl N

-------
REFERENCES

Bormann, F. H. , G. E. Likens, D. W. Fisher, and R.  S.  Pierce.
     1968.  Nutrient Loss Accelerated by Clear-Cutting of a
     Forest Ecosystem.  Science 159: 882-884.

Brink, N. , and A. Gustafson.  1970.  Lantbrukshogskolan.
     No. 1, Institutionenen for Markvetenskap-Vattenvard,
     Uppsala, Sweden.

Cole, D. W. , and Gessel, S. P.  1965.  Movement of Elements
     through a Forest Soil as Influenced by Tree Removal and
     Fertilizer Additions.  In: Youngberg, C. T. (ed.).
     Forest-Soil Relationships  in North America.  Oregon State
     Univ. Press, Corvallis , Ore.  p. 95-104-.

Cooke, G. D. , T. N. Bhargava, M. R. McComas , M. C.  Wilson, and
     R. T. Heath.  1973.  Some  Aspects of Phosphorus Dynamics
     of the Twin Lakes Watershed.  In: Modeling the Eutrophi-
     cation Process.  Middlebrooks , E. J.  (ed.).  Pub. PRWG136-1,
     Utah Water Research Lab.,  Utah State Univ., Logan, Utah.
     p. 57-72.

Cooper, C. F.  1969.  Nutrient  Output from Managed Forests.  In:
     Eutrophication:  Causes, Consequences,  Correctives.  National
     Academy of Sciences, Washington, B.C.  p.  M-H6-463.

Daniel, H. A., H. M.  Elwell, and H. J. Harper.  1938.  Nitrate-
     Nitrogen Content of Rain and  Runoff Water  from Plots under
     Different Cropping Systems on Vermon  Fine  Sandy Loam.
     Soil  Sci. Soc. Amer. Proc. jk 230-233.

Jaworski,  N. A.,  and  L. J.  Hetling.   1970.  Relative Contri-
     butions  of Nutrients to the Potomac River  Basin from
     Various  Sources.  Tech. Rep.  31, Middle Atlantic  Region,
     Federal Water Pollut.  Con. Adm.  36 p.

Sylvester, R. 0.   1961.  Nutrient  Content  of Drainage  Water from
     Forested, Urban  and Agricultural Areas.  Tech. Rep.' W61-3,
     Trans.  1960  Seminar  on Algae  and Metropolitan Wastes,
     Robert  A. Taft  San.  Engr.  Ctr. ,  Cincinnati, Ohio.   p.  80-87.

Taylor, A. W., W.  M.  Edwards,  and  E.  C.  Simpson.   1971.
     Nutrients in Streams Draining Woodland and Farmland near
     Coshocton,  Ohio. Water  Resources  Res.  Kl): 81-89.

Viro,  P.  J.   1953.   Loss  of Nutrients and  the Natural  Nutrient
     Balance of  the  Soil  in Finland.  Comm.  Inst.  Forest,  Fenn.
                              59

-------
           NUTRIENT  LOSSES  FROM MARSHES AND WETLANDS
Nutrient  dynamics  of  marshes and other wetland areas is one
of the more poorly-defined  aspects of nutrient transport from
watersheds; the  role  of  wetlands as nutrient sources or sinks
for down-gradient  water  bodies has not been established satis-
factorily.   Several factors enhance the potential of marshes
to act as nutrient sinks.   Flow velocities through marsh
systems are generally low so, if a marsh receives runoff water,
settling  removes a large portion of the suspended particulate
materials;  high  levels of photosynthesis, characteristic of
wetlands, incorporate nutrients into plant tissue; and nitrogen
removal also occurs through denitrification reactions.  On the
other hand, the  periodic occurrence of anaerobic conditions
increases the possibility for discharge of ammonia and soluble
inorganic phosphorus, particularly in wetlands subject to
pulses of high discharge from runoff.

The development  of nutrient budgets for wetlands has been
hampered  by the  complex  hydrology of marsh areas.  Groundwater
seepage often accounts for  the majority of water input, evapora-
tion accounts for  much of the output, and the rates of water
exchange  by these  mechanisms has proven to be very difficult
to measure.

Bentley (1969) studied four marshes in Wisconsin and estimated
that on a long-term basis,  they were neither nutrient sources
nor sinks,  but that the  marshes tended to accumulate nutrients
during the  growing season and released them during spring
runoff.   However,  even during periods of active photosynthesis,
the marshes were not  a barrier to nutrient transport; concen-
trations  of dissolved inorganic phosphorus in discharge waters
typically exceeded 0.01  mg/1.  Bentley also reported that
nitrate was largely removed from input waters through denitri-
fication  and plant uptake.  Nitrogen in the discharge waters
was  in  the  form  of ammonia or organic nitrogen, the majority
being in  the organic  form.

Based on  laboratory leaching studies, Amundson (1970) concluded
that the  practice  of  draining marshes negated most beneficial
effects and agravated the effects detrimental to water quality.
He estimated that  phosphorus runoff from drained marsh lands
may be as large  as 5  kg/ha/yr—an amount equal to 10-20 times
the normal  contribution  from agricultural lands.
                             60

-------
Water quality characteristics of marshes (managed for northern
pike spawning) adjacent to Houghton Lake, Michigan were studied
by Novy and Pecor (1973).  Typical management operations were
to pump lake water into the marshes in early spring and drain
them about two months later.  This operation was repeated in
the fall.  Nutrient budget computations showed that the marshes
received about 0.04 kg/ha more inorganic nitrogen than was
discharged and, conversely, there was a net release of 0.04 kg/ha
of phosphorus to the lake.  Operations during the study year
were atypical, and it was estimated that, under normal condi-
tions , there would be no net phosphorus flux to the lake and
the loss of inorganic nitrogen in the marsh would be somewhat
larger than 0.4 kg/ha.

Based on these studies, it is estimated that the runoff co-
efficients for both phosphorus and nitrogen are approximately
zero for wetlands; however, the range of conditions studied
is too restrictive to establish the general validity of these
findings.


REFERENCES


Amundson, R. W.  1970.  Nutrient Availability of a Marsh Soil.
     M.S. Thesis, Water Chemistry Dept., Univ. of Wisconsin,
     Madison, Wis.  56 p.

Bentley, E. M.  1969.  The Effect of Marshes on Water Quality.
     Ph.D. Thesis, Water Chemistry Dept., Univ. of Wisconsin,
     Madison, Wis.  197 p.

Novy, J. R., and C. H. Pecor.  1973.  Impact of Northern Pike
     Spawning Marsh Operation on Water Quality.  Tech. Bull.
     73-2, Michigan Water Resources Com. and the Dept. of
     Natural Resources, Lansing, Mich.  40 p.
                              61

-------
              NUTRIENT INFLUX FROM GROUNDWATER


Nutrient contributions from direct groundwater influx are
one of the most poorly defined components of lake nutrient
budgets and, based on the fragmentary information available,
these contributions can be very significant.  The mobility
of inorganic nitrogen in soil-water systems, along with the
relatively high concentrations of nitrogen found in many
groundwaters, has led to the general consensus that direct
seepage through lake beds could account for a large portion
of the total nitrogen loading for some lakes (Vollenweider,
1968; Lee, 1970; Keeney, 1972).  Lee et al (1969) estimated
that  36% of the total nitrogen influx to Lake Mendota re-
sulted from direct groundwater seepage.

Phosphorus influx via groundwater seepage is generally thought
to be quite small.  Lee et al (1969) estimated that only
about 2% of the phosphorus entering Lake Mendota was carried
by seepage.  Cooke et al (1973) measured nutrient budgets for
East  Twin and West Twin Lakes (Ohio) and reported data showing
that  groundwater influx accounted for  3.2 and 7.5% of the
phosphorus entering these lakes respectively over an 18-month
period.

Somewhat larger relative phosphorus contributions from ground-
water have been reported for  two small lakes in Wisconsin.
Based on field studies, Hennings  (1974)  estimated that 24% of
the phosphorus (and 72% of water) enter  Pickerel Lake by
seepage.  Possin (1973) reported similar groundwater contri-
butions of 25% phosphorus and 21% water  for Mirror Lake.
This  latter study also indicated that  the absolute input of
total phosphorus was  also quite significant and  amounted to
about 0.12 gm-P/ha/yr.  A summary of these  data  is given in
Table 14.

In very general terms, groundwater  contributions are functions
of 1) the nutrient concentrations in the surrounding aquifers,
2) the extent of groundwater  exchange  between  lake and aquifer,
and 3) biochemical modification of  nutrient  forms  during
seepage through the permeable material surrounding the lake,
including the bottom  sediments.  Of these,  nutrient concentra-
                             62

-------
Table 14.  NUTRIENT  CONTRIBUTIONS TO LAKES
              VIA GROUNDWATER

0)

nj
£j
 
c s 06
-HO -P O

OP14-1 dP <4-l
11%
25%
72% 44%
21% 34%
M
M \
4J 0) g
!3 -P gO*
ft nS 0
C 5 H -
•H -d M-l M
§0)
C7>-P
O C CO
i— 1 M -H ^
cd D^ 'C T3
o g 00
•P O HO
5-1 M
<*P IH S tn
3.2%
7.5%
24% 1.4
25% 1.74
\
CM
.4
O
M -
0)
tJ* -P
C *d
•H ^
^ 'O
10 C
o 9
H 0

cu (T*
.023
.027
.033
.12

a)
o
a
a)
5-1
o
m
a)
OJ
Cooke et
1973
Cooke et
1973
Hennings
Possin,









al.
al,
, 1974
1973
                     63

-------
tions in the surrounding aquifer can be determined most
readily.  The latter two considerations present considerably
more difficulty.

Water budget measurements have been used to calculate ground-
water exchange with lakes (Allred et al, 1971; Salo and
Cooperman, 1972), but the accuracy of this technique is
often limited by difficulties associated with the determina-
tion of evaporation losses—a second "unknown" in the water
budget equation.  More importantly, the budget approach gives
only net exchange, and this information may be insufficient
from the standpoint of nutrient loadings.  For example, Born,
Smith and Stephenson (1974) compiled data for 64- lakes in
glaciated, temperate regions of North America and reported
that 40% of these were "flow-through" lakes with respect to
groundwater, i.e. groundwater inflow and outflow occurred
simultaneously within the lakes' basins.  Water budget studies
would underestimate the magnitude of groundwater influx in
lakes of this type.

Stephenson (1971) modified results presented by Walesh (1966)
and compiled a list of techniques that could be used for
investigating groundwater-surface water exchange, and dis-
cussed the applicability of these techniques to lakes.  (See
Table  15.)  He emphasized that field investigations are neces-
sary to establish the degree of water exchange between lakes
and surrounding aquifers.  A thorough discussion of the hydro-
logic regime of glacial-province lakes, including a classi-
fication scheme for various types of groundwater exchange with
lakes, is given by Born, Smith and Stephenson (1974).

The relative contributions of groundwater to the water budget
of 22 lakes are given in Table  16.  These data illustrate the
wide range of conditions which occur and emphasize the need
for on-site investigations if one is to account for nutrient
influx—and outflow—via subsurface water movement.

Even when quantities of groundwater exchange are known, the
role of lake sediments in altering nutrient constituents of
seepage waters must be taken into account when estimating
loadings.  Keeney et al (1971) measured denitrification rates
in sediments using 15N-labeled nitrate and, based on in-situ
experiments in Lake Mendota, they estimated that two-thirds
of the nitrate entering the lake by seepage would be "lost"
from the lake system because of denitrification in the lake
sediments.  (It is possible that groundwater seepage through
lake sediments has a greater impact on lakes by providing a
mechanism for enhancing nutrient recycling, than it does by
                             64

-------
                              Table  15. PARTIAL LIST OF METHODS FOR INVESTIGATING
                                    THE GROUNDWATER-SURFACE WATER INTERCHANGE
en
en
Factors required in application of method










Method of study
Analytical (mathematical)
Hydrologic balance
Flow net
Numerical (digital)

Well equations
Electrical
Resistance network
analog
Conductive solid

Conductive liquid

Physical

Sand tank
Hele-Shaw



o
42 i-l
O M 60
•HO O
6C y vH
o tu o
*0 1 £ 2
•$ M £ *

X
useful useful
X

X

X
X

X



X
X



§§
Jj tf^
CO 4J
>. p.

M
> U
o co
t-< 4)


X
X

X

X
X

X



X
X


^•j
4-1
•H
*W4
•H
Q
 O
« g
4J 5
II








X

X (with
2-D
flow)


X
X
0)
t-l (0
n 
-------
                 Table 16.   GROUNDWATER CONTRIBUTIONS TO THE WATER BUDGET OF LAKES
CT)
Lake name
Oyster Pond
Lake Sallie
Pitcher Lake
Booster Club
Pond
Mud Lake
Ria Lake
Lake Poinsett
Krause Pond
Sunshine Springs
Snake Lake
Pickerel Lake
Mirror Lake
Shadow Lake
Location
near Woods Hole,
Mass
Becker Co, Minn
near St. Paul/
Minn
Anoka Co, Minn
Sibley Co, Minn
near Newport,
Minn
Hamlin Co, Minn
Langlade Co, Wis
Langlade Co, Wis
Vilas Co, Wis
Portage Co, Wis
Waupaca Co, Wis
Waupaca Co, Wis
Area <
(ha)
25
486
3
3
13
4
3965
0.4
0.4
6
16
4
16
Max
depth
(m)
6
17
3
2
2
2
5
4
4
5
5
14
14
gw inflow
tot inflow
83%
14%
-
-
-
-
10.30%
^100%
^100%
50%
72%
21%
41%
gw outflow
tot outflow
0(?>
0
(net) 15%
(net) 18%
(net) 10%
(net) 40%
2%
0
0
>0
?
16%
2%
Reference
Emery (1969)
Mann & McBride
(1972)
Allred et al (1971)
n „ (i97i)
ii n » (i97i)
11 " (1971)
Barari (1971)
Carline (1973)
(1973)
Born et al (1973)
Hennings (1974)
Possin (1973)
(1973)

-------
          Table 16 con't.  GROUNDWATER CONTRIBUTIONS TO THE WATER BUDGET OF LAKES
Lake name
Jyme Lake
East Twin
West Twin
Little
St. Germain
Muskellunge
Lake
Qui ns i g amond
Deep Lake
Lake Lenore
Soap Lake
Location
Oneida Co, Wis
Portage Co, Ohio
Portage Co, Ohio
Vilas Co, Wis
Vilas Co, Wis
Worchester Co,
Mass
Grand Coulee,
Wash
Grand Coulee ,
Wash
Grand Coulee,
Wash
Area
(ha)
0.4
27
34
384
111
312
49
445
336
Max
depth gw inflow
(m) tot inflow
3 0
12 11%
12 25%
5 24%
6 44%
26 (net) 20-60%
98%
33%
84%
gw outflow
tot outflow
^30%
0
0
0
0

0
9%
8%
Reference
Smith et al (1972)
Cooke et al (1973)
ii » (1973)
Hackbarth (1968)
(1968)
Salo & Cooperman
(1972)
Friedman &
Redfield (1971)
Friedman &
Redfield (1971)
Friedman &
Redfield (1971)
Modified from Born, Smith and Stephenson  (1974)

-------
adding nutrients from outside sources.  However, only this
latter aspect is considered here.)

Considering the present state of knowledge, there appear to
be no general guidelines for the estimation of nutrient
influx via groundwater.  More research is needed in this
area, particularly for flow-through lakes where a net loss
of nutrients could occur even though there may be a net
addition of water to a lake.  Direct management applications ,
such as the location of septic tanks in areas where ground-
water movement is away from lakes, add further support for a
better definition of the groundwater regime of lake systems.
                             68

-------
REFERENCES


Allred, E. R., P. W. Hanson, G. M. Schwartz, P.  Golany,  and
     J. W. Reinke.  1971.  Continuation of Studies on the
     Hydrology of Ponds and Small Lakes.  Tech.  Bull. 274,
     Univ. of Minnesota, Agr. Exp. Sta., St. Paul, Minn.

Barari, A.  1971.  Hydrology of Lake Poinsett.  Rept. Inv.
     102, South Dakota Geological Survey, Vermillion, S.D.

Born, S. M. , S. A. Smith, and D. A. Stephenson.   1974._  The
     Hydrogeologic Regime of Glacial-Province Lakes, with
     Management and Planning Applications.  Inland Lake Renewal
     and Management Demonstration Project Report, Dept.  of
     Natural Resources and the Univ. of Wisconsin, Madison,
     Wis.

Born, S. M., T. L. Wirth, J. 0. Peterson, J. P.  Wall, and
     D. A. Stephenson.   1973.  Dilutional Pumping at Snake
     Lake, Wisconsin—A  Potential Renewal Technique  for
     Small Eutrophic  Lakes.  Tech. Bull.  66, Dept. of Natural
     Resources, Madison, Wis.

Carline,  R.  F.   1973.  Spring  Pond Research—A Progress Report.
     Dept. of  Natural Resources,  Madison, Wis.

Cooke,  G.  D.,  T.  N. Bhargava,  M.  R. McComas,  M.  C. Wilson,
     and  R.  T.  Heath.  1973.   Some Aspects  of Phosphorus
     Dynamics  of the  Twin  Lakes Watershed.   In:  Middlebrooks,
     E. J.,  D.  H.  Balkenborg,  and T. E. Maloney  (eds.).
     Modeling  the Eutrophication  Process.   PRWG136-1, Proc.
     Workshop, Utah State  Univ.,  Utah  Water Research Lab.,
     Logan,  Utah.   p. 57-72.

Emery,  K.  0.   1969.   A  Coastal Pond  Studied by Oceanographic
     Methods.   American  Elsevier, New  York.

Friedman, I.,  and A.  C.  Redfield.  1971.  A Model of the
     Hydrology of the Lakes of the  Lower Grand  Coulee,
     Washington.   Water  Resources Res. 7_(4) : 874-898 .

Hackbarth, D.  A.  1968.   Hydrogeology  of the Little St.
      Germain Lake Basin, Vilas County, Wis.  M.S.  Thesis,
      Univ. of Wisconsin, Madison, Wis.

Hennings, R. G.  1974.   A Hydrologic Investigation of the
      Pickerel Lake Basin, Portage County, Wisconsin.  M.S.
      Thesis, Univ. of Wisconsin,  Madison, Wis.
                              69

-------
Keeney, D. R.  1972.  The Fate of Nitrogen in Aquatic Eco-
     systems.  Literature Review No.  3,  Water Resources
     Center, Univ. of Wisconsin, Madison,  Wis.

Keeney, D. R., R. L. Chen, and D. A.  Graetz.   1971._  Im-
     portance of Denitrification and  Nitrate  Reduction in
     Sediments to the Nitrogen Budget of Lakes.   Nature
     233:66-67.

Lee, G. F.  1970.  Eutrophication.  Occasional Paper^No. 2,
     Water Resources Center, Univ.  of Wisconsin,  Madison,
     Wis.

Lee, G. F. (chrm.).  1969.  Report on the  Nutrient Sources
     of Lake Mendota.  Lake Mendota Problems  Committee,
     Madison, Wis.

Mann, W. B. , IV, and M. S. McBride.   1972.  The Hydrologic
     Balance of Lake Sallie, Becker County, Minnesota.
     Prof. Paper 800-D, U.S. Geologic Survey.  p. D189-D191.

Possin, B. N.  1973.  Hydrogeology of Mirror  and Shadow Lakes
     in Waupaca Co., Wisconsin.   M.S.  Thesis, Univ.  of Wiscon-
     sin, Madison, Wis.

Salo, J. E. , and A. N. Cooperman.  1972.   Lake Quinsigamond
     Water Quality Study—1971.   Pub.  6306, Massachusetts
     Water Resources Com., Div.  of Water Pollut.  Con.

Smith, S. A., J. 0. Peterson, S. A. Nichols,  and S.  M. Born.
     1972.  Lake Deepening by Sediment Consolidation—Jyme
     Lake.  Univ. of Wisconsin and Wisconsin  Dept. of
     Natural Resources, Inland Lake Demonstration Project,
     Madison, Wis.

Stephenson, D. A.  1971.  Groundwater Flow System Analysis
     in Lake Environments, with Management and Planning
     Implications.  Water Resources Bull.  7_( 5) : 1038-1047.

Vollenweider, R. A.  1968.  Scientific Fundamentals of the
     Eutrophication of Lakes and Flowing Waters, with Par-
     ticular Reference to Nitrogen and Phosphorus as Factors
     in Eutrophication.  Pub. DAS/CSI/68.27,  Organisation for
     Economic Cooperation and Development, Directorate for
     Scientific Affairs, Paris, France.

Walesh, S. G.  1966.  Ground Water-Surface Water Interchange—
     A Summary of Methodology.  Unpub. Independent Study,
     Geol. 999, Univ. of Wisconsin, Madison,  Wis.
                             70

-------
          NUTRIENT CONTRIBUTIONS FROM SEPTIC TANKS


Traditionally, the criteria for assessing the adequacy of
septic tank/soil absorption systems have been related to
health considerations.  Design specifications or conditions
for approval (permit requirements) of on-site domestic waste
treatment systems generally relate to the presence of soil
types with infiltration capacities sufficient to prevent
surface discharge of effluent and to prevent contamination
of drinking water supplies.  Nutrient migration from soil
absorption fields has been of concern only recently.

A compilation and review of data describing the composition
of household wastewater are given by Ligman et al (1974).
Considering bath, toilet, kitchen and laundry, household
wastewaters contain about 6.5 kg-N and 1.5 kg-P per capita
("average adult") per year.  These values were based on
fulltime occupancy, and 50% of the phosphorus originated
from the laundry.  Therefore, lesser loadings would be ex-
pected for septic tanks serving seasonal lakeshore properties.
Ellis and Childs  (1973) reported the phosphorus load in house-
hold wastewater to be about 0.5 kg/capita/year without laundry
and 1.6 kg/capita/year with laundry.

Nutrient attenuation  in the soil absorption field is dependent
upon the loading  rate, permeability and absorption capacity
of the soil, depth of overburden above the water  table, and
groundwater movement  in the saturated zone.  Bouma et al  (1972)
showed that the formation of crusts in the seepage field
greatly altered performance by reducing infiltration rates
20- to 100-fold and permitting unsaturated conditions to
persist in seepage beds.  Ellis and Childs  (1973) documented
the down-gradient migration of nitrate and phosphorus for dis-
tances up to 100  and  43 meters from drain fields, respectively.

Field measurements of the amount of phosphorus  adsorbed
to soils in septic tank seepage beds around Houghton Lake,
Michigan are also reported by Ellis and Childs  (1973).  Maxi-
mum observed values for four soil  types—expressed as mg-P/kg
of soil—are given below.
                              71

-------
                                Observed maximum
            Soil type            (mg-P/kg soil)

            Rifle peat                  50
            Newton loamy sand        ~ 120
            Rubicon sand               135
            Nester loam              150-300
The influence of phosphorus retention capacity on the migra-
tion of phosphorus from septic tank systems is illustrated
by the following data presented by Ellis and Childs (1973).
Each site received a "high" phosphorus loading, and the data
columns refer to values obtained within 3 m of the drainfields,
or at distances greater than 13 m from the drainfields.
Depth
(m)
0-0.3
0.3-0.7
0.7-1.0
1.0-1.3
Newton loamy
P-retention,
(3m) (
151
117
121
102
sand
mg/kg
13m)
84
79
17
18
Rifle peat
P-retention, mg/kg
(3m)
19
18
7
1H
(13m)
4
23
8
5
      after  Ellis  and  Childs (1973)

The Newton  loamy  sand adsorbed much of the phosphorus input
and still retained some adsorption capacity at 13 m from the
drainfield.  The  Rifle peat showed much lower phosphorus re-
tention, indicating that phosphorus was migrating through the
soil to the lake; this was documented by groundwater sampling.

A conservative (high) estimate of nutrient loadings to lakes
from septic tank  seepage can be computed by applying the
factors 1.5 kg-P/capita/yr and 6.5 kg-N/capita/yr to each
lakeshore dwelling served by septic tank systems.  These values
can be reduced, when appropriate, to account for seasonal
occupancy, lack of laundry facilities, areas where ground-
water movement is away from the lake, and phosphorus retention
capacity of soils.  Phosphorus retention efficiencies range
from nearly 100%  in loamy soils to almost zero for older
systems in peat or light sand.
                             72

-------
REFERENCES


Bouma, J., W. A. Ziebell, W. G. Walker, P. G. Olcott,  E.  McCoy,
     and F. D. Hole.  1972.  Soil Absorption of Septic Tank^
     Effluent, a Field Study of Some Major Soils in Wisconsin.
     Information Circular No.  20, Univ. of Wisconsin-Extension,
     Madison, Wis.  235 p.

Ellis, B., and K. E. ChiIds.   1973.  Nutrient Movement from
     Septic Tanks and Lawn Fertilization.  Tech. Bull. No. 73-5,
     Dept. of Natural Resources, Lansing, Mich.  69 p.

Ligman, K., N. Hutzler, and W. C. Boyle.  1974.  Household
     Wastewater Characterization.  J.  Environ. Engr. Div., ASCE.
     100(EE1):201-213.
                              73

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    ATMOSPHERIC CONTRIBUTIONS OF NITROGEN AND PHOSPHORUS


Data were compiled which describe the quantity of nitrogen
and phosphorus contributed annually via bulk precipitation
at locations throughout the continental United States.   Bulk
precipitation is defined to include rainfall, snowfall, and
dry fallout (dust fall).  All data were converted to a rate
of nutrient input expressed in kg/ha/yr.  Data presented
originally as nutrient concentrations in rainfall were con-
verted by multiplying the concentrations by appropriate
conversion factors and the 30-year average rainfall for that
location as compiled and published in the National Atlas by
the U.S. Geological Survey for the years 1935-1965.  A large
amount of nitrogen data was found.  However, because of the
scarcity of phosphorus data specific to the United States,_
data for other locations were included as well.  Lake loading
values can be computed by multiplying the tabulated coefficients
by the surface area of a lake.

Two related approaches were utilized in this phase of the
study:  1) a compilation of data for specific locations and
2) a cartographic approach based on nitrogen concentrations
in precipitation.


FACTORS AFFECTING NUTRIENT CONTENT OF BULK PRECIPITATION

The .majority of authors found that a simple parts-per-million
measurement of the constituents of rain was a less accurate
prediction of eventual total contribution of nutrients than
such factors as geographic location, agricultural land use,
and season.  Two prominent authors, Yaalon (196M-) and Junge
(1958), have suggested a relationship between acidity and
temperature of the soil and total final contribution.  Unfor-
tunately, each study seems to suggest correlations and
hypotheses distinct to that area of study.

In an early study in Ottawa, Shutt (1925) reported that "there
was no direct proportionality between the volume of rainfall
or snowfall and the quantity of nitrogen furnished annually
per acre."  Since then, numerous confirming studies have been

-------
reported.  Matheson (1951) concluded there "were no simple
correlations with atmospheric conditions" in his study in
Hamilton, Ontario.  Gambell and Fisher (1966) found similar
results in Virginia and concluded "no single present theory
seems adequate to explain the characteristics shown by the
network NO3 data."  Allen et al (1968) also confirmed this
lack of correlation from studies in England where he found
"periods of very high rainfall are associated with greater
quantities of the elements but that the converse is also
true	I can see no consistent pattern in months'
fluctuations across sites in either occurrences or magni-
tudes."  The only study that proposed a correlation (r = 0.91)
was conducted by Chojnachi and M. Kac Kacas (1966) in the
Pulway Region of the Soviet Union.  Unfortunately, only the
abstract has been translated into English.

This lack of correlation is the result of many factors, and
dry fallout appears to be of critical importance.  Whitehead
and Feth (1964) estimated that between four to ten times the
nutrient content of rain falls as bulk precipitation.
Eriksson (1952), after exhaustive testing in Scandinavia,
concluded that fallout may contribute three times as much
nitrogen as precipitation.  Matheson  (1951) determined that
dry fallout comprises 4-0% of the total nitrogen contribution
from the atmosphere for Canada, while Junge  (1958) estimated
that 70% of the atmospheric nitrogen  contribution in arid
climates comes from dry fallout.  Kluesener  (1972) found
that for Madison, Wisconsin the nitrogen  contribution  from
dry fallout is double that of precipitation, while for phos-
phorus it is up to three times that of rainfall.

Distribution of precipitation between rain and  snow has also
been cited as an important factor.  Shutt  (1925)  and Barica
and Armstrong  (1971) in their Canadian studies  found that
snow contributions were considerable  and  that concentrations
in snow  (water equivalent) may be significantly higher than
in rain.  In their findings snow contributed from one-fourth
to over  one-half  of the total, although  snow comprised a  far
smaller  proportion of total precipitation.

Gore (1968)  analyzed rainfall over  a  six-year period_at Moor
House  in northern England, and presented  data which  illustrate
annual variations at one  site.
                              75

-------
Year
1959-60
1960-61
1961-62
1962-63
1963-64
1964-65
Ave
Rain
cm
179
191
203
186
179
176
186
Inorganic-N
kg/ha/yr
-
-
10.7
12.5
14.5
18.6
14.0
Total-P
kg/ha/yr
0.3
0.9
0.3
1.8
0.6
1.1
0.8
         after  Gore  (1968)
Another study conducted in England by Allen et al (1968)
illustrates geographical variations in atmospheric contri-
butions of nitrogen and phosphorus.
Study site
40 km from sea
( 8 km from chemical plant)
Forested lake district
15 km from sea
Open moorland
19 km from North Sea
Coniferous forest
8 km from North Seas
Rain
cm/yr
95
174
162
172
95
116
Nutrient contributions
kg/ha/yr
Total-N Total-P
19.0 0.8
0.3
9.5 0.4
8.7 0.3
8.9 0.2
13.0 0.8
after Allen et al (1968)

The contribution of phosphorus via bulk precipitation has been
studied less intensively than nitrogen because, for both agri-
culture and lake management, other sources of phosphorus are
likely to be more important.  Schraufnagel et al (1967) esti-
mated that only 1.2% of the phosphorus found in Wisconsin waters
was contributed by precipitation, and Sridharan (1972) estimated
that the contribution of phosphorus via bulk precipitation in
                             76

-------
Green Bay was only .5% of the total.  Gore (1968) noted that
the scarcity of data resulted from the relative unimportance
of atmospheric sources and aerial pathways of nutrients and
that limited research has generated "insufficient data" so
far, to draw conclusions as to the possible sources of rain-
water phosphorus.  From a study of two sites in England he
speculated that possible extraneous sources were household
dust and smoke.

In addition to scarcity of data, sampling problems and tem-
poral and regional variations of phosphorus concentration in
precipitation complicate data interpretation.  Gore (1968)
reported that phosphorus utilization by microorganisms can
result in a 30% underestimation of the phosphorus content
unless a preservative such as iodine is added to sampling
vessels.  He also reported that bird defecation  causes serious
sampling problems.

Several researchers reported considerable seasonal variations
in the phosphorus content of rain.  Reimbold and Daiber (1967)
sampled rainfall in Delaware and found phosphorus concentra-
tions in summer to be more than 20 times those found in late
winter and spring.They attributed these variations to  "unusual
phosphorus cycles found in the bay areas and marshes along the
eastern United States."  They also stress the influence of
agricultural activity during spring planting and of dust from
unpaved roads.  Tamm  (1951) also identified these contributory
factors.  Allen et al (1968) found peak concentration  to occur
in December, March and June in England, and also noted that
"the phosphorus quantity showed no  consistent close relation-
ship with the quantity of rain, except occasionally for the
extremely high and low rainfalls."  Kluesener  (1972) conducted
studies in Wisconsin  and found that highest concentrations
occurred in May which he attributed to seeds, birds, and
pollen.  In England,  Carlisle et al  (1966)  also  identified
these sources as  contributing to increases  in phosphorus con-
centrations.  Particularly high concentrations,  about  5 times
those reported in most Western countries, were reported by
Vijayalakshmi and Pandalai  (1962) in  India  during the  monsoon
season.

Although considerable differences were noted between findings
of the  various investigators, there are some areas in  which
consensus has been reached.   It is  generally agreed that storms
and prevailing winds  off the  ocean  are low  in phosphorus con-
tent  and that the major  source of phosphorus in  rainfall is
from  dust generated  over the  land.  Urbanization and indus-
trialization  are  cited by  Voigt  (I960) and  others  as major
contributors.  Soil  erosion,  industrial ash, and smoke are
also  commonly  listed.
                              77

-------
Unfortunately, data interpretation is complicated by sig-
nificant differences which exist between the various studies
reported.  In some, only the contribution from rainfall was
measured; gaging instruments were closed during periods of
no rain.  Others used open gages that measured both dustfall
and rainfall, and some were constructed to handle snowfall.
In addition, techniques for chemical analyses have changed
considerably during the time span of the reported studies ,
which greatly complicates data interpretation; only recent
papers express concern for nitrogen loss through denitrifica-
tion, or shifts in chemical species during sample storage
prior to analysis.

Data describing atmospheric contributions of nitrogen and
phosphorus are summarized in Tables 17 and 18 respectively.
These tables contain more than 125 determinations of the
annual atmospheric contribution of nitrogen in its various
forms at some 60 locations in the United States and Canada
and over 33 values of phosphorus loadings throughout the
World.  These represent the measurements of more than 50
scientists over a period of 50 years and can be taken as
independent data points for checking the reasonableness of
estimations presented in this paper and of any on-site experi-
mental results of nitrogen and phosphorus contribution from
the atmosphere.  Care, however, must be taken to incorporate
the information provided in the footnotes for these tables
because only then are the numbers comparable.


CARTOGRAPHIC PRESENTATION OF NITROGEN CONTRIBUTIONS
FROM PRECIPITATION

The most comprehensive research regarding the nitrogen content
of rainfall was reported by Junge (1958).  In this paper, he
reported concentrations of nitrate and ammonia at over 60 gaging
stations across'the United States.  Data were grouped into
seasonal concentrations of four three-month periods over the
year from July 1955 to July 1956.  The study was designed so
that results would be comparable with those found by Eriksson
(1952) in his investigations of precipitation in Scandinavia.
As a result, gages were located at U.S. weather stations away
from large urban areas and industrial sites and were designed
to record only precipitation and not bulk fallout.  They were
also equipped with a heating device to melt ice and snow.

A common problem in gaging experiments of this type is to keep
organic matter out of the collection receptors (Gore, 1968).
The primary source for such organic matter is bird droppings,
                             78

-------
                       Table 17.  ATMOSPHERIC  CONTRIBUTIONS  OF  NITROGEN3
Study
                         Rainfall
                            cm
-J
to
Northeastern U.S.
  Windsor, Conn
  Washington, B.C.
  New Brunswick, N.J.
  New Jersey
  Albany, N.Y.
  Geneva, N.Y.
  Geneva, N.Y.
  Ithaca, N.Y.
  Ithaca, N.Y.
  Ithaca, N.Y.
Southeastern U.S.
  Tallahassee, Fla
  Cape Hatteras, N.C.
  Cape Hatteras, N.C.
  (120 mi at sea)
  Greenville, N.C.
  N. Carolina - high
  N. Carolina - ave
  N. Carolina - low
  N. Carolina-Virginia
  Roanoke, Va
                            140
                            137
                            121
                            119

                            121


                            127
N contribution in kg/ha/yr
N03-N     NIU-NTotal N
                                                          4.5
                  Reference
105

115
91
100

100
100
75
5
5

8

6
1
1
8
.1
.6

.4

.7
.1
.4
. 0
0.
5.
3.
1.
8.


4.
4.
6
6
3
5
6


5
1


9.2

10.1




 2.3
 3.2
 0.5
 8.0
 2.71
 l.?l
 0. 51
 1.4
 8.9
0. 8
1.2

1.0

1.3



0.51

  2J_|
 • T
                             Jacobson et al (1948)
                             Junge £ Werby (1958)
                             Prince et al (1941)
                             Malo & Purvis (1964)
                             Junge £ Werby (1958)
                             Collison et al (1933)
                             Bizzell (1944)
                             Wilson (1921)
                             Leland (1952)
                             Buckman £ Brady (1961)
Junge £
Junge £
Gambell
Junge £
Gambell
Gambell
Gambell
Gambell
Junge £
Werby (1958)
Werby (1958)
£ Fisher (1964!
Werby (1958)
£ Fisher (1966;
£ Fisher (1966;
£ Fisher (1966;
£ Fisher (1964;
Werby (1958)

-------
                   Table 17  continued.   ATMOSPHERIC CONTRIBUTIONS OF NITROGENa
CO
o
Rainfall N contribution in
Study
Midwest U.S.
Urbana, 111
Urbana, 111
Indianapolis , Ind
Kentucky
Kentucky
Duluth, Minn
Columbia, Mo
Columbia, Mo
Cincinnati, Ohio
Coshocton, Ohio
Coshocton, Ohio
Coshocton, Ohio
Coshocton, Ohio
Hancock, Wis
LaCrosse, Wis
LaCrosse, Wis
Madison, Wis
Madison, Wis
Madison, Wis
Madison, Wis
Madison, Wis
cm

94
94
100
112

80
. 102
102
110
78
89
89
93
45
43
116
44
102
107
90
-
N03-N NHi,-N

2.3 0.7

4.6 2.1
8.0
0.8
1.8 1.9-4.7
8.7 3.5

0.2-15.4°
17.5°
20.0°
20. Oc
20. 9C






3.1 2.8
6.5b 6.8b
kg/ha/yr
Total N


1.7





22.4b





4.1
7.2
9.6
4.5
19.6
16.7
7.7
23. Ob

Reference

Junge & Werby (1958)
Larson & Hettick (1956)
Junge 6 Werby (1958)
Freeman (1924)
Johnson (1925)
Putnam S Olson (1960)
Junge S Werby (1958)
Woodruff (1949)-
Weibel et al (1964)
Taylor et al (1971)
Taylor et al (1971)
Taylor et al (1971)
Taylor et al (1971)
Shah (1962)
Shah (1962)
Shah (1962)
Shah (1962)
Shah (1962)
Shah (1962)
Kluesener (1972)
Kluesener (1972)

-------
                   Table 17  continued.   ATMOSPHERIC  CONTRIBUTIONS  OF NITROGENa
CO
   Study
Rainfall
   cm
   Midwest  U.S.  con't
     Marshfield, Wis
     Marshfield, Wis
     Milwaukee,  Wis
     Sturgeon Bay, Wis
     West-Central Wis •
     rural
     West-Central Wis •
     urban
H  West/Southwest  U.S.
     Fresno,  Calif
     Riverside,  Calif
     San  Diego,  Calif
     Grand  Junction, Colo
     Glasgow,  Mont
     Ely, Nev
     Guthrie,  Okla
     Goodwell, Okla
     Oklahoma
     Amarillo, Tex
     Brownsville,  Tex
     Tacoma,  Wash
    69
    86
    52
   100
    90

    90
  N contribution in kg/ha/yr
  N03-N     NH4-N    Total N
                        4.2
                       13.1
                        4.4
                       18.5
                  Reference
                  Shah (1962)
                  Shah (1962)
                  Shah (1962)
                  Shah (1962)
2.8-3.5b  2.9-12.2b 13.2-30.lb Hoeft (1971)
   3.7b
            1.6
3.6b
             4.1
28
23
38
38
75
46
50
53
64
203
1.9
1.3
3.3
0.7
1.1
0.6
0.8
2.0
2.5
4.6
2.4
0.6
2.2
1.0



1.2
1.4
0.8
13.5b   Hoeft (1971)
                  Junge 8  Werby (1958)
        9.0-14.6   Broadbent 8  Chapman  (1950)
                  Junge 8  Werby (1958)
                  Junge 8  Werby (1958)
                  Junge 8  Werby (1958)
                  Junge 8  Werby (1958)
                  Daniel et al (1938)
                  Finnel & Houghton (1931)
                  Finnel & Houghton (1931)
                  Junge &  Werby (1958)
                  Junge &  Werby (1958)
                  Junge 8  Werby (1958)

-------
                   Table 17  continued.  ATMOSPHERIC CONTRIBUTIONS OF NITROGEN*
oo
N3
Study
Canada
Hamilton, Ont
Hamilton, Ont
Ottawa, Ont
Ottawa, Ont
Ottawa, Ont
Ottawa, Ont
Northwest Ontario
Northwest Ontario
Rainfall
cm



60
62
(snow)
snow
snow
N contribution in kg/ha/yr
N03-N

1.8
3 . 7b
2.4
2.0
0.5

NIU-N Total N

3.2
6.5b
5.0
4.4
0.8
4 . 4b 7 . 8b
(4.3)d
(5.8b)d
Reference

Matheson (1951)
Matheson (1951)
Buckman & Brady (1961)
Shutt S Hedley (1925)
Shutt £ Hedley (1955)
Shutt (1925)







Barica S Armstrong (1971)
Armstrong 8 Shindler( 1971)
   Footnotes:
   a -  Unless  noted, all values are for rainfall only.
   b -  bulk precipitation
   c -  NO3  + NHi,
   d -  data for 4 months only

-------
                     Table 18.   ATMOSPHERIC CONTRIBUTIONS OF PHOSPHORUS3
CD
co
    Study
North America
  New Haven, Conn
  Delaware
  Cincinnati, Ohio
  Kent, Ohio
  Northwest Ontario
  Northwest Ontario
  Green Bay, Wis
  Madison, Wis
  Madison, Wis
Other
  Australia, Melbourne
  Czechoslovakia
  England
  England
  England - high
  England - ave
  England - low
  France
  Gambia
                        Rainfall
                           cm
                               100
   P contribution
	kg/ha/yr	
Inorganic    Total
          Reference
                              snow
                              snow
  0.18
  0.33b
 0.10     Voigt (1960)
 0.56     Reimbold & Daiber (1967)
 0.80     Weibel et al (1966)
 0.14-     Cooke et al (1973)
(0.40b)c  Armstrong & Shindler (1971)
(0.27b)c  Barica 8 Armstrong  (1971)
 0.08     Sridharan (1972)
 0.23     Kluesener (1972)
                                                   1.02°

                                                   0. 30
                                                 0.07-0.16
                                                   0.20
                                                   O.U3
                                                   1.09
                                                   0.85
                                                   0.12
                                                   0.40
                                                   0.17
          Kluesener (1972)

          Attwill (1966)
          Chalupa (1960)
          Allen et al (1968)
          Carlisle et al  (1966)
          Gore  (1968)
            tt      it
            Tl      It
          Farrugia (1960)
          Thornton (1965)

-------
                Table 18  continued.   ATMOSPHERIC CONTRIBUTIONS  OF PHOSPHORUS*
00
    Study
                        Rainfall
                           cm
Other con't
  Germany
  Ghana
  India, Kerala
  Italy
  Nigeria
  Russia, Voronezh
  Scandinavia
  Scandinavia
  South Africa, Natal
   P contribution
      kg/ha/yr
InorganicTotal
                               100
             0.13
             3.3
             4.75
            1.6-2.0
            0.4-2.6
             0.3
           0.15-0.50
             1.0
             8.0
                                                        Reference
Ottermann £ Krzysch (1965)
Nye (1961)
Vijayalakshmi 6
Pandalai (1962)
Imporato (1964)
Jones (1960)
Sviridova (1960)
Tamm (1951)
Tamm (1953)
Ingham (1943)
    a - Unless noted, all values are for rainfall only.
    b - bulk precipitation
    c - data for four winter months only

-------
which has forced many investigators to construct elaborate
gaging vessels that must be continually cleaned and checked
for the presence of bird defecation by testing for abnormally
high phosphorus concentrations.  This care is important
because not only will the presence of such matter give very
high ammonia readings, but it also increases the chances for
denitrification to occur.  Junge (1958) avoided problems of
bird waste by having the collectors covered except during
the time of actual precipitation, which accounts for the
absence of dry fallout information also.  Denitrification
was kept to a minimum by using plastic containers which per-
mitted exchange of oxygen, and samples were stored no longer
than 30 days prior to analysis.

Consideration of factors which could potentially influence
Junge's results leads to the conclusion that, if the data
are not truly representative, they are biased toward under-
estimating the nitrogen content of rainfall.

One possible source of error results from the manual operation
of the rain gages.  Individuals housed at the gage sites were
to keep the gages covered until the rains began, at which
point the sampling vessels were to be uncovered.  However,
as Gambell and Fisher (1964) and others have pointed out, the
concentration of nutrients in rain water, especially ammonia,
is highest at the beginning of storms and declines very rapidly
thereafter.  Gambell and Fisher found very rapid washout in
the first minutes of a storm when ammonia concentration dropped
from 8 to 1 ppm.  This phenomenon was especially pronounced
in storms of high turbulence and intensity.  Angstrom and
Hoberg (1952) described this decline in concentration as an
exponential reduction with time.  Therefore, it would appear
that even if the gages were left covered for only a short time
at the beginning of storms, considerable ammonia could have
been lost.

Site location could also significantly influence results.
Hoeft (1971) showed that the proximity to agricultural animal
concentrations is a dominant factor in nutrient contributions.
Also, organic nitrogen is relatively high in these situations.
Junge located his collection sites at the outskirts of urban
areas and in small towns to avoid industrial concentrations.
These sites were probably located near sparse animal concen-
trations.  Therefore, in states with high animal concentrations
in the rural areas, Junge's data probably underestimate the
nutrient contribution from the atmosphere.
                              85

-------
 Junge's  results were presented in map form with isobars
 separating  the country  into regions of uniform concentration
 of  nitrogen in precipitation.  Each map represented a three-
 month  period, and nitrate and ammonia were mapped separately.
 These  concentrations were converted to loadings (kg/ha/yr)
 in  this  study by using  30-year averages for monthly precipi-
 tation at the sampling  sites.  It should be noted that in
 some instances exact sampling locations are not given in the
 1958 paper  of Junge and Werby or in three previous papers,
 Junge  (1956), (1958a),  (1958b), which describe the methodology
 for the  project.

 Loadings for nitrate and ammonia were computed separately and
 then combined to cover  a one-year period.  These combined
 data points were transferred to a map (Figure 2 ) and isobars
 of  equal contributions  in terms of kg/ha/yr were drawn under
 the assumption of linear transformation between data points.
 The gradient between isolines is 0.5 kg/ha/yr.  This increment
 was selected to show the relative pattern of loadings ; the
 approach used is not sufficiently accurate to justify further
 interpolation.  These patterns are suggestive of general
 input  distribution but may be subject to considerable local
 variation.

 Based  on Figure 2, the region bordering the southern Great
 Lakes  receives the largest input of nitrogen from atmospheric
 sources, and loading values  on the order of 3.0-3.5 kg N/ha/yr
 were calculated.   However, as discussed above, it is likely
 that the values  shown in this figure are underestimates of
 the actual  loading.   Dry fallout was not included in the
 calculations, and it has been estimated that this factor
 could  account for 40-90% of  the nitrogen input (Hoeft, 1971;
 Kluesener,   1972).   A comparison of the loading rates shown
 in  Figure 2 with  the data in Table 17 shows considerable dis-
 crepancies   at some locations and, in general, it appears that
 the loading rates  shown in Figure 2 are low by a factor of
 3 or 4.  If this  is  the case, then the Great Lakes region
 of  the United States may receive an atmospheric contribution
 of  nitrogen at a  rate of about 10 kg/ha/yr.  This corresponds
 to  the permissible loading rate of 1.0 g/m2/yr for lakes with
mean depths less  than 5 meters (Vollenweider, 1968).  It
would appear, therefore, that for this region of the country,
 it  may be extremely  difficult to limit the influx of nitrogen
to  levels considered permissible or satisfactory from the
standpoint  of controlling eutrophication in shallow lakes
because atmospheric  contributions alone could be large.
                             86

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                                                                                           2.0 kg/ha/yr
00
-0
                                 Fig.  2.   NITROGEN CONTRIBUTIONS
                                 (N03-N & NH^-N) FROM RAINFALL

-------
Although Figure 2 gives only a general estimate of atmospheric
nitrogen contributions, some guidelines are available for
judging the significance of local conditions.  Parameters for
these locational variations cannot be identified with sufficient
precision to predict the magnitude of a specific influence;
however, enough is known from the literature to permit the
construction of a matrix indicating the direction of change
resulting from identifiable factors.  In this manner, Table 19
may be used as a guide for refining local estimations in the
absence of direct measurements.  Approximately forty factors
which influence atmospheric contributions are listed.  A "+"
sign indicates that the presence of a given condition tends
to give higher nutrient inputs via bulk precipitation, a "-"
sign indicates lower inputs, and a "0" is used to indicate
no effect.  A discussion of many of these factors is given
by Kluesener (1972).

A comparison of factors listed in Table 19 suggests that atmo-
spheric contributions of both nitrogen and phosphorus are
likely to increase in the future.  Agricultural and industrial
development, activities certain to increase, tend to increase
atmospheric nutrient contributions, whereas factors which lead
to lower contributions are primarily natural phenomena, not
likely to change and generally beyond the control of man.
This trend is also supported somewhat by data presented in
this report.  Of the five study sites where studies were con-
ducted for prolonged periods, higher contributions were
detected in later years in all instances.  Also, the station
of longest continuing record at Ottawa, Canada was abandoned
because encroaching industry, intensive agriculture and urban
development gave rise to nutrient concentrations higher than
those recorded in the past.  This may have been the result
of truly local influences; however, it may also be indicative
of more general trends.  Nevertheless, atmospheric contribu-
tions of nitrogen and phosphorus appear to be more significant
than is generally recognized with respect to control of lake
eutrophication, and these contributions are likely to be
larger in the future.
                             88

-------
co
to
                     Table 19 .   INFLUENCE OF LOCAL CONDITIONS ON NUTRIENT
                                CONTRIBUTIONS FROM THE ATMOSPHERE
Condition
1. Existence of intensive
agriculture
2. Animal feedlots and/or
high local agricul-

Nitrogen
+
+
Influence on
Reference
Attshuller '58
Mattson et al '5
Yaalon '64
Hoeft '71
Hoeft et al '72
atmospheric contribution
Phosphorus
5 +
Reference
Reimbold et al
Carlisle et al
'67
'66
       tural animal pop
    3.  Industrial activity
Hutchenson e.a.'69
Firbas '52
Junge '58
Mattson et
Shutt '25
Voigt '60
al '55
    U.  Urbanization
    5.  Automobile concen-
       tration

    6.  Power plants and/or ex-
       plosives factories,
       fertilizer factories

    7.  Solid waste disposal
       plants and sites
Eriksson '52
Firbas '52
Gorham '61
Shutt '25
Voigt '60
Harkins et
Myers '70
al '67
Junge '56
Shy et al '70
Myers '70

-------
                Table 19  continued.   INFLUENCE OF LOCAL CONDITIONS ON NUTRIENT
                               CONTRIBUTIONS  FROM THE ATMOSPHERE
                                          Influence on atmospheric contribution
       Condition
    8.  Heavy precipitation in
       given year relative
       to previous years
    9.  Duration of in-
       dividual storms


   10.  Predominance of short
       intense rainfalls
   11.  Frequent presence  of
Q      fog and dew
   12.  Thunderstorms
       prevalent
Nitrogen
   13.  Inshore  ocean winds
    Reference

Chilingar '56
Chojnacki '64
Daniel et al
Matheson '51
                                                           Phosphorus
                       38
         Kluesener '72
         Angstrom et al
         Wetselaar et al
               '52
                '63
         At twill
         Matheson
        '66
         '51
         Eriksson '52

         Gambell '63
         Gambell et al '64
         Gambell et al '66
         Hutchinson '57
         Junge '58
         Virtanen '52

         Eriksson '52
         Gambell '63
         Gambell et al '64
         Gambell et al '66
         Hutchinson '57
         Junge '58
         Lodge et al '68
     Reference


Allen et al '68
Vijayalakshmi e.a.'62
                               Reimbold et al '67

-------
CD
                Table 19  continued.   INFLUENCE  OF LOCAL CONDITIONS ON NUTRIENT
                               CONTRIBUTIONS  FROM THE ATMOSPHERE
       Condition
                                          Influence  on atmospheric contribution
                           Nitrogen
   14.  Turbulent  storms
       (create  dust  prior
       to  rain)


   15.  Distance inland from
       major  body of water
16.  Predominance of snow
    as form of
    precipitation


17.  Arid conditions -
    dry soil

18.  Tropical conditions


19.  Polar conditions


20.  Variations in yearly
    temperature of soil
    (highest contributions
    from warming soils)

21.  Saturated, poorly
    areated soil

22.  High exchange capacity
    of soils
    Reference

Gambell et al '66
Kluesener '72


Gambell et al '66
Junge '58
Thornton '65

Barica et al '71
Herman et al '57
Kluesener '72
Shutt '25

Attshuller '58
Junge '58

Angstrom et al '52

Angstrom et al '52
Lodge et al '68
                                       Allison  '55
                                       Yaalon  '64
                                       Attshuller  '58


                                       Allison  '55
Phosphorus
Reference
                                                                   Thornton '65
                                                                      Vijayalakshmi  e.a.'62

-------
             Table 19  continued.   INFLUENCE OF LOCAL CONDITIONS ON NUTRIENT
                            CONTRIBUTIONS FROM THE ATMOSPHERE
                                       Influence on atmospheric contribution
    Condition
         Nitrogen
23.  pH of soil
Alkaline

Acid
24.  Weathered soil,
    especially prairie


25.  Soils with high humus
    content


26.  Tidal marshes


27.  Forested areas


28.  Unpaved roads


29.  Prevalence of grass
    and forest fires

30.  Heavy bird populations

31.  Northern latitude

32.  High altitude
                               •f

                               +
    Reference

Allison '55
Junge '58
Kluesener '72
Malo et al '64

Allison '55
Bizzell '43

Allison '55
Attshuller '58
Yaalon '64
                                    Tamm !51
                                    Voigt '60
                  Gore '68
                  Shutt '25

                  Gore '68

                  Junge '58

                  Junge '58
                                                        Phosphorus
Reference
                                                 Reimbold et al '67

                                                 Carlisle et al '66
                                                 Tamm '51

                                                 Reimbold et al '67
                                                 Thornton '65

-------
REFERENCES

Allen, S. E., A. Carlisle, E. J. White, and C. C. Evans.
     1968.  The Plant Nutrient Content of Rainwater.  J. Ecol.
     5j3_:497-504.

Allison, F. E.  1955.  The Enigma of Soil Balance Sheets.  In:
     Advances in Agronomy 7.  Academic Press, New York, N.Y.
     p.  231-250.

Angstrom, A., and  L. Hoberg.  1952.  On the Content of Nitrogen
     (NH4-N and N03-N) in Atmospheric Precipitation.  Tellus
     4_(1) :31-42.
Armstrong, F. A. J. , and D.  W. Schindler.  1971.  Preliminary
     Chemical Characterization of Waters in the  Experimental
     Lakes Area, Northwestern Ontario.  J. Fish. Res. Bd. Can.
     _
Attshuller, A.  P.   1958.   Natural Sources  of  Gaseous Pollutants
     in  the Atmosphere.   Tellus  .10:479-490.
Attwill,  P. M.   1966.   The Chemical Composition of  Rainwater
     in  Relation to the Cycling  of Nutrients  in Natural
     (Mature)  Eucalyptus.  Plant and Soil  24: 390-406.

Barica,  J., and F.  A.  J.  Armstrong.  1971.   Contribution of
     Snow to  the Nutrient Budget of Some Small Northwest
     Ontario  Lakes.  Limnol.  and Oceanog.  16; 891-899.

Bizzell,  J. A.   1943.   Comparative Effects of Ammonium Sulfate
     and Sodium Nitrate on Removal of Nitrogen and  Calcium
     from Soil.  Mem.  252, Agr.  Exp . Sta. , Cornell  Univ.,
     Ithaca,  N.Y.   p.  1-24.
Bizzell,  J. A.   1944.   Lysimeter Experiments, VI. The ^ Effects
     of  Cropping and Fertilization on the Losses of Nitrogen
     from the Soil.  Mem. 256, Agr. Exp. Sta., Cornell Univ.,
     Ithaca,  New York.  p. 1-14.
Broadbent, F. E. , and H. D. Chapman.  1950.  A Lysimeter  Inves-
     tigation of Gains, Losses and Balance of Salts and Plant
     Nutrients in an Irrigated Soil.  Soil Sci. Soc. Amer.
     Proc. 14:261-269.
Buckman, H.  0., and N. C. Brady.   1961.  The Nature and
      Properties of Soils.  6th ed.  The MacMillan Co., New
     York, N.Y.  567 p.
 Carlisle, A.  A., H. F. Brown, and  E. F. White.  1966.  The
      Organic and Nutrient Elements in the Precipitation  beneath
      Sessile Oak Canopy.  J. Ecol. _54: 87-98.
                              93

-------
 Chalupa,  J.   1960.   Eutrophication  of Reservoirs  by Atmospheric
      Phosphorus.   Fac.  Tech.  Feul Water  4,1.   Inst.  Chem.
      Tech.,  Prague.   p.  295-308.

 Chilingar,  G.  V.   1956.   Durvov's Classification  of Natural
      Waters  and the  Chemical  Composition of Atmospheric  Pre-
      cipitation in the  USSR:  A Review.   Amer.  Geophys. Union
      Trans.  37:193-196.

 Chojnacki, A.   1964.  Nutrient Elements  for Plants  in Atmo-
      spheric Precipitation.   Postepy Nauk roln 11:101-112.

 Chojnacki, A.,  and M. Kac Kacas.  1966.  Investigations  on the
      Content of Plant Nutrients in Atmospheric Precipitation
      in the  Pulway Region.  Roczn Nauk roln 92A;77-89 .

 Collison, R.  C. , H. G. Beattie, and J. D. Harlan.   1933.
      Mineral and Water Relations and Final Nitrogen  Balance
      in Legume  and Nonlegume  Crop Rotations for a Period of
      16 Years.  Tech. Bull. 212, Agr. Exp. Sta., Geneva, N.Y.
      p. 1-81.

 Cooke,  G. D., T. N. Bhargava,  M.  R.  McComas, M. C. Wilson, and
      R. T. Heath.  1973.  Some Aspects of Phosphorus Dynamics
      of the  Twin Lakes Watershed.   In: Modeling the  Eutrophi-
      cation  Process.   Middlebrooks,  E. J. (ed.).  Pub. PRWG136-1,
      Utah Water Research Lab., Utah  State Univ., Logan,  Utah.
      p. 57-72.

Daniel, H. A., H. M.  Elwell, and H.  J. Harper.  1938.  Nitrate-
     Nitrogen Content of Rain  and Runoff Water from  Plots
     under Different  Cropping  Systems on Vermon Fine Sandy Loam.
     Soil Sci. Soc. Amer. Proc.  3_:230-233.

Eriksson,  E.   1952.   Composition of  Atmospheric Precipitation:
     I. Nitrogen Compounds;  II.  Sulphur,  Chloride, Iodine
     Compounds.  (A Bibliography)  Tellus 4_:3-4.

Farrugia.   1960.  (Unknown.   See Vollenweider, 1968, p.  112.)

Finnell, H.  H. , and H.  M. Houghton.   1931.   Soil Nitrogen
     Income  from Rainwater.   Bull.  23, Pan.  Agr.  Exp. Sta.,
     Oklahoma.

Firbas, F.  1952.  Einige Berechnungen urber die Ernahrung
     der Hochmoor.  Veroff.  Geobot.  Inst. Zurich 25:177-200.
                             94

-------
Freeman, J. F.  1924.  Nitrogen in the Rainwater of Different
     Parts of Kentucky.  J. Amer. Soc. Agron. 16:356-358.

Gambell, A. W.  1963.  Sulfate and Nitrogen Content of
     Precipitation over Parts of North Carolina and Virginia.
     Paper 475-C, U.S. Geolog. Survey.  p. C209-C211.

Gambell, A. W., and D. W. Fisher.  1964.  Occurrence of Sulfate
     and Nitrate in Rainfall.  J. Geophys. Res. _6_9: 4203-4210.

Gambell, A. W., and D. W. Fisher.  1966.  Chemical Composition
     of Rainfall, Eastern North Carolina and Southeastern
     Virginia.  Water  Supply Paper 1535K, U.S. Geolog. Survey.
     p. 1-41.

Gore, A. J. P.  1968.  The Supply of  Six-Elements by Rain to an
     Upland Peat Area.  J. Ecol. 56:483-495.

Gorham, E.  1961.  Factors Influencing Supply of Major Ions
     to Inland Waters, with Special Reference to the Atmosphere.
     Geolog.  Soc. Amer. Bull. 72:795-840.

Harkins, J. H. , and S. W. Nicksic.  1967.  Ammonia in Auto
     Exhaust.  Environ. Sci. Technol. !_: 751-752.

Herman, F. A., and E.  Gorham.   1957.  Total  Mineral  Material,
     Acidity, Sulphur  and Nitrogen in Rain and Snow  at
     Kentville, Nova Scotia.  Tellus  9^:180-183.

Hoeft,  R.  G.  1971.  Atmospheric Contribution of S and N.
     Ph.D. Thesis, Soils Dept., Univ. of Wisconsin,  Madison,
     Wis.

Hoeft,  R.  G., D. R.  Keeney,  and L. M. Walsh.   1972.  ^Nitrogen
     and Sulfur Dioxide  in the  Atmosphere  in Wisconsin.  J.
     Environ. Quality  .1:203-208.

Hutchenson,  G. L., and F.  G.  Viets, Jr.   1969.  Nitrogen
     Enrichment of Surface Waters by  Absorption of Ammonia
     Volatilized from Cattle Feed Lots.   Science 166:514-515.

Hutchinson,  G. E.  1957.   A  Treatise  on Limnology, Vol. 1 -
     Geography, Physics  and  Chemistry.   John Wiley and Sons,
     New York, N.Y.

Imporato,  Gargano.   1964.  Ammonia, Nitrate, Nitrite, Phosphate,
     and  Sulphate  Contents  of Rainwater.  Ann.  Fac.  Agr.
     Portici 29:369-378.
                              95

-------
Ingham, G.  1943.  The Fertility of the Air.   South Africa
     J. Sci. 39_:35-43.

Jacobson, H. G. M., C. L.  W.  Swanson,  and E.  Smith.  1948.
     Effects of Various Fertilizer Cations and Anions on
     Soil Reaction Leaching Nitrification of  Urea,  and Related
     Characteristics in an uncropped Soil. Soil Science
     6_5:437-460.

Johnson, E. M.  1925.  Analysis  of Rainfall from a  Protected
     and an Exposed Gage for  Sulfur, Nitrate  Nitrogen, and
     Ammonia.  J. Amer. Soc.  Agron.  17:589-591.

Jones, E.  1960.  Contribution of Rainwater to the  Nutrient
     Economy of Northern Nigeria.   Nature, London,  England
     188,432.

Junge, C. E.  1956.  Recent Investigations in Air Chemistry.
     Tellus 8^:127-139.

Junge, C. E.  1958a.  Chemical Analysis of Aerosol  Particles
     and of Gas Traces on the Island of Hawaii.  Tellus 9:
     528-537.

Junge, C. E.  1958b.  The Distribution of Ammonia and Nitrate
     in Rainwater over the United States.  Trans. Amer.
     Geophys. Union 39:241-248.

Junge, C. E., and R. T. Werby.  1958.   The Concentration of
     Chloride, Sodium, Potassium,  Calcium, and Sulphate in
     Rain Water over the United  States.  J. Meteorol. 15:
     417-425.

Kluesener, J. W.  1972.  Nutrient Transport and Transformation
     in Lake Wingra, Wisconsin.   Ph.D. Thesis, Water Chemistry
     Dept., Univ. of Wisconsin,  Madison, Wis.

Larson, T. E. , and I. Hettick.  1956.   Mineral Composition of
     Rainwater.  Tellus 8^:191-201.

Leland, E. W.  1952.  Nitrogen and Sulfur in  the Precipitation
     at Ithaca.  Agron. J. 44:172-175.

Lodge, J. P., et al.  1968.  Chemistry of the United States
     Precipitation.  Final Rep., National Precipitation Sampling
     Network, Lab. of Atmospheric Res., Boulder, Colo.  66 p.

Malo, B. A., and E. R. Purvis.  1964.  Soil Absorption of
     Atmospheric Ammonia.  Soil Science 97:243-247.
                             96

-------
Matheson, D. H.  1951.  Inorganic Nitrogen in Precipitation
     and Atmospheric Sediments.  Can. J. Technol. 29 :406-412.

Mattson, S., and E. Koutler-Anderson.  1955.  Geochemistry
     of a Raised Bog, II. Some Nitrogen Relationships.
     Lantbr. Hogsk Ann. 22:219-224.

Myers, P. S.   1970.  Automobile Emissions, a Study in Envirpn-
     mental Benefits versus Technological Costs.  (January 12-16,
     1970)  SAE, Automotive Engineering, Detroit, Mich.

Nye, P. H.  1961.  Organic Matter  and Nutrient Cycles under
     Moist Tropical Forests.   Plant  and Soil 13:333-346.

Ottermann, A., and G.  Krzysch.   1965.  The N, P, K, Ca, and SOi,
     Contents  of Rain  Water  in Dahlem.  Z. Pflernahr. Dung.
     Bodenk 111:122-131.

Prince, A.  L. , S.  J.  Toth, A.  W.  Blair, and  F. E. Bear. _  1941.
     Forty-Year Study of  Nitrogen Fertilizers.   Soil  Science
     52:247-261.

Putnam,  H.  D., and T.  A.  Olson.   1960.  An  Investigation  of
     Nutrients in  Western Lake Superior.  Sch.  of Public  Health,
     Univ.  of Minnesota,  Minneapolis,  Minn.

Reimbold,  R.  J.,  and F. C.  Daiber.  1967.   Eutrophication of
     Estuarine Areas by Rainwater.  Chesapeake  Science
      8^:132-133.

Schraufnagel, F.  H.  (chrm.).  1967.  Excess Water Fertilization
      Report   Working Group on Control Techniques,  Res. on
      Water Fertilization, Water Subcommittee _ of Natural Resources
      Committee of State Agencies, Madison,  Wis.

 Shah,  K. M.   1962.  Sulfur and Nitrogen Brought Down in
      Precipitation in Wisconsin.  M.S. Thesis, Soils Dept.,
      Univ. of Wisconsin, Madison, Wis.

 Shutt  F  T    1925.  Report of the  Dominion Chemist for Year
      Ending'March 31,  1925 (17-year series).  Dept. of
      Agriculture, Domion of Canada.  p. 68-74.

 Shutt  F. T., and B.  Hedley.   1925.  The Nitrogen Compounds in
      Rain and Snow.   Proc. Royal  Canadian Institute, Ser. IIIA
      19:1-10.
                               97

-------
Shy,  C.  M. , J. P.  Creason, M. E. Pearlman, K. E. McClain,
      F.  B. Benson,  and M. M. Young.  1970.  The Chattanooga
      School Children's Study: Effects of Community Exposure
      to  Nitrogen Dioxide. Part I - Methods; Description of
      Pollutant Exposure and Results of Ventilatory Function
      Testing.  J.  Air Pollut. Con. Assoc. 20 :539-545.

Shy,  C.  M. , J. P.  Creason, M. E. Pearlman, K. E. McClain,
      F.  B. Benson,  and M. M. Young.  1970.  The Chattanooga
      School Children's Study: Effects of Community Exposure
      to  Nitrogen Dioxide. Part II - Incidence of Acute
      Respiratory Illness.  J. Air Pollut. Con. Assoc. 20:
      582-588.

Sridharan, N.  1972.  Aqueous Environmental Chemistry of
      Phosphorus in  Lower Green Bay, Wisconsin.  Ph.D. Thesis,
      Water Chemistry Dept, , Univ. of Wisconsin, Madison, Wis.

Sviridova, I. K.   1960.  Results of a Study of the Leaching
      of  Nitrogen and Mineral Elements by Rain from the Crowns
      of  Tree Species.  Dokl. akad. nauk 133:706-708.

Tamm, C. 0.  1951.   Removal of Plant Nutrients from Tree Crowns
      by  Rain.  Plant Physiol.  4_: 184-188.

Tamm, C. 0.  1953.   Growth Yields and Nutrition in Carpets
      of  a Forest Moss.   Medd Stat. Skogdforskn. Inst. 43:
      1-140.

Taylor, A. W. , W.  M. Edwards,  and E. C. Simpson.  1971.
     Nutrients in Streams Draining Woodland and Farmland near
      Coshocton,  Ohio.  Water Resources Res. J7: 81-89.

Thornton, I.   1965.  Nutrient Content of Rain Water in Gambia.
     Nature 205:1025.

Vijayalakshmi, K. ,  and  K.  M. Pandalai.  1962.  Nutrient Enrich-
     ment of the Coconut Soils of the Humid Kerala Coast
     through Monsoon Precipitation.  Nature 194:112.

Virtanen, A.  I.   1952.   Molecular Nitrogen Fixation and the
     Nitrogen Cycle in  Nature.  Tellus 4_: 304-306.

Voigt, G. K.   1960.  Distribution of Rainfall under Forest
     Stands.   Forest Science
Voigt, G. K.  1960.  Alteration of the Composition of Rainwater
     by Trees.  Amer. Midland Nat.  63:321-326.
                             98

-------
Vollenweider, R. A.  1968.  Scientific Fundamentals of the
     Eutrophication of Lakes and Flowing Waters, with Par-
     ticular Reference to Nitrogen and Phosphorus as Factors
     in Eutrophication.  Reference DAS/CSI/68.27, Organisation
     for Economic Cooperation and Development, Directorate for
     Scientific Affairs, Paris, France.

Weibel, S. R. , R. J. Anderson, and R. L. Woodward.  1964.
     Urban Land Runoff as a Factor in Stream Pollution.
     J. Water Pollut. Con. Fed. 36:914-924.

Weibel, S. R., R. B. Weidner, J. M.  Cohen, and A. G.
     Christiansen.  1966.  Pesticides and Other Contaminants
     in Rainfall and Runoff.  J. Amer. Water Works Assoc.
     58:1075-1084.

Wetselaar, R. , and J. T. Hutton.  1963.  The Ionic Composition
     of Rain Water at Katherine N.T.  and Its Part in the  Cycling
     of Plant Nutrients.  Australian J. Agr. Res. 1M-: 319-329.

Whitehead, H. C. ,  and J. H.  Feth.  1964.   Chemical Character
     of Rain, Dry  Fallout,  and Bulk  Precipitation at Menlo
     Park, California,  1957-1959.  Geophys. Res.  69(16):
     3319-3333.

Wilson, B. D.   1921.  Nitrogen  in the Rain Water  at  Ithaca,
     New  York.   Soil  Science 11:101-110.

Woodruff,  C. M.   1949.   Estimating the  Nitrogen Delivery of
     Soil from  the Organic  Matter Determination as  Reflected
     by Sanborn Field.   Soil Sci. Soc.  Amer.  Proc.  14:208-212.

Yaalon, D. H.   1964.   The  Concentration of Ammonia and Nitrate
     in Rain Water over Israel  in Relation to Environmental
     Factors.   Tellus 16:200-204.
                              99

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                           SUMMARY
It is apparent from the data tabulated in this report that con-
siderable variation exists in the quantities of nutrients that
are exported from "similar" areas devoted to the same use.  In
considering the contributions of nutrients from diffuse sources,
and considering the flow of water to be the primary transport
mechanism, it would be expected that important contributing
factors would include:

1.  General topography, particularly contour.

2.  Precipitation characteristics, including:  total annual
amount; seasonal distribution; duration, frequency and intensity
of storms; and snowfall/runoff.

3.  Soil properties, including:  chemical exchange characteris-
tics, mineral composition, grain size distribution, antecedent
soil moisture, and hydraulic properties such as permeability.

4.  Vegetative cover, including:  type, density and permanence.

5.  Manipulative practices, such as paving, plowing, flooding,
and fertilizing.

6.  Animal populations—type and density.

Other factors could also be identified, but of those listed,
only the latter three groups relate  directly to land use.
Although topography, precipitation, and soil characteristics
influence to some extent the use which is made of particular
lands, these factors generally do not impose restrictions that
severely limit the range of possible uses.  Therefore, land use
designations do not account for these parameters, and additional
studies are needed to develop techniques for including them in
the estimation procedure.  This could be accomplished by refined
subdivision of drainage areas and the measurement of corre-
sponding nutrient loss or, possibly, by the development of
guidelines for selecting appropriate nutrient flux coefficients
which incorporate these parameters in addition to land use
information.

Those data most applicable for estimating nutrient loadings from
non-point sources are listed below and referenced to tables
included in the previous sections.
                             100

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     Contributions from:             Tables       Pages

     Diffuse sources:
        agricultural lands              9         36-38
        urban areas                    11           ^9
        forested lands                 13           58
        wetlands and marshes                      60-61
     Groundwater transport                        62-68

     Bulk precipitation             17 & 18       79-84

     Miscellaneous:
        manure handling                           40-42
        animal populations             10           41
        septic tanks                              71-72


Based on the results of nutrient transport studies reported
here, there appears  to be little justification for the delinea-
tion of land usage within direct drainage basins beyond four_
categories:  urban,  forested, agricultural, and wetlands.  With
one possible exception—agricultural  lands, the available data
are too fragmentary  and variable to warrant further specifica-
tion of use categories.  Armstrong et al  (1974) estimated that
on the basis of surface runoff  studies,  agricultural lands could
be further subdivided and thet  the following  flux coefficients
might be considered  "average" values.
                           Nitrogen  loss,       Phosphorus loss,
                             kg-N/ha/yr          kg-P/ha/yr

                          N03+NHi+  Total-N     Piss  Inorg Total-P
Row crops
Close-grown crops
Pasture £ meadow
Idle (fallow) land
1.6
1.7
2.3
3.9
37.
15.
2.5
67.
0.21
0.13
0.22
0.05
1.62
0.47
0.24
1.23
 after Armstrong et al (1974)

 The coefficients for the soluble inorganic nutrient forms  compare
 reasonably well with corresponding values determined from  stream-
 flow studies.   However, the coefficients for runoff of total N
 and total P are much larger than those determined by streamflow
 studies, and the usefulness of these data for purposes of  esti-
 mating lake loadings is questionable.
                              101

-------
 Nutrient runoff values  for urban,  forested  and  agricultural
 areas (streamflow studies  only)  are  plotted in  Figures  3b,
 3c and 3d,  respectively.   Figure 3a  is  a  plot of the  baseline
 conditions  and key,  which  are  used to provide a perspective
 for the runoff data.  Throughout the discussion which follows ,
 only diffuse sources  of nutrients  are considered;  atmospheric
 input is ignored; and it is  assumed  that  drainage  basins  are
 devoted to  only one  use.

 The abscissa for all  plots is  nitrogen  export from watershed
 areas in kg/ha/yr; ordinate  values are  the  ratio of nitrogen
 export/phosphorus export.  The plotted  data points refer  to
 paired values of dissolved inorganic phosphorus and nitrate
 plus ammonia-nitrogen (open  circles) or total phosphorus  and
 total nitrogen (solid circles).

 For discussion purposes, the plots are  subdivided  by  horizon-
 tal and radial lines.   The horizontal lines define areas  where
 N/P > 15, 15 > N/P >  10, and N/P < 10.  Based on the  nutri-
 tional requirements of  algae,  it might  be expected that algal
 populations  in lakes  which receive nutrient loadings  with
 N/P > 15 would tend to  be phosphorus-limited.   Conversely, if
 N/P < 10, nitrogen limitation might be  expected.   Obviously,
 this is a gross  simplification which applies to lake  environ-
 ments in only a  cursory way; but the concept is used  here to
 illustrate some  of the  differences and  similarities of runoff
 waters  from  lands of  various use categories.

 The  radial lines on the plots are based on  a "permissible"
 specific lake  loading rate of 1.5 g-N/m2/yr and 0.1 g-P/m2/yr
 (these  rates  are equivalent to 15 kg-N/ha/yr and 1.0  kg-P/
 ha/yr).  Each  radial line refers to a given ratio  of  direct
 drainage basin area/lake surface area,  and  lines for  ratios
 of  1,  3, 5,   10, and 50 are shown.  Data points which  lie  to the
 right  (clockwise) of any radial line refer  to loading rates
which would  exceed both permissible loading limits given  above;
points  to the  left of any radial line refer to  loading rates
which are less than these limits.

For  example, the open data point in Figure  3a corresponds to
nutrient flux coefficients  of about 3 kg-N/ha/yr and  a coef-
ficient ratio, N/P, of about 23 (i.e.,  a phosphorus loss  of
about 3/23 = 0.13 kg-P/ha/yr).   The location of the point on
the plot indicates that flux coefficients of this magnitude
would result in permissible loading rates in those situations
where basin  areas are only 5 times as large as the receiving
lake; but the permissible loading limit would be exceeded if
the basin areas are 10 or more times as large as the  lake.
                             102

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H
o
CO
              ro
              in
              O
              rH

              CO
O
.C
PL,
w
O
x:
DL,
\
en
w
o
              0)
              bO
              O
              k
              •p
              •H
                N/P =
              o

             _o N/P

             -M

             &,
       = 10
   Total  N£P

O Dissolved Inorganic NSP
                                            X^^iP-Limit at ion
               Figure  3a.
            0          2          14          6          8          10
                              Nitrogen  loss  in kg/ha/yr

              FORMAT  FOR COMPARING NUTRIENT RUNOFF COEFFICIENTS

-------
o
-p
                       Figure 3b.
                6          8

    Nitrogen loss in kg/ha/yr

NUTRIENT EXPORT FROM URBAN AREAS
                                                                       10
12

-------
Figure 3c
      U          6         8
    Nitrogen loss  in  kg/ha/yr
NUTRIENT EXPORT  FROM.  FORESTED LANDS
                                                10
12

-------
                                                                         <3
O
cn
                     Figure 3d.
       4          6          8          10

         Nitrogen loss  in  kg/ha/yr

NUTRIENT LXPORT FROM AGRICULTURAL LANDS
                                                                                 12

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In addition, the runoff would be relatively rich in nitrogen
so that there may be a tendency toward phosphorus limitation
in the receiving waters.

Runoff coefficients for urban areas are plotted in Figure 3b. ^
Although only six data points are available, this plot dramati-
cally illustrates the very fertile nature of urban runoff.  Not
only is this runoff very high in phosphorus on a relative basis,
it is also high in both nitrogen and phosphorus in absolute
terms.  Very small drainage  areas—basin-to-lake area ratios
of unity or less—are sufficient to provide excessive amounts
of nutrients.

In comparison, nutrient runoff  from forested lands (Figure  3c)
is far less intense.  Considering only dissolved inorganic
nutrient forms, runoff from  forested areas would not approach
the specified  loading limit  unless the drainage area was more
than 10 times  as  large as  the lake and, in some cases, area
ratios as large as 40 would  not cause excessive loadings.   It
is interesting to note that  the soluble inorganic  constituents
of forest drainage are high  in  nitrogen relative to phosphorus,
whereas the opposite is true for the majority of cases when
total nutrient forms are  considered.

A greater degree  of variability is shown  by the data from
agricultural drainage studies  (Fig. 3d).   On a  relative basis,
most studies showed that  agricultural drainage  was^high in
nitrogen.   Considering  only  soluble inorganic nutrient forms,
basin/lake  area ratios  as  small as  2 or  as  large as 40 resulted
in nutrient runoff values  that  approached the permissible limit
specified.

Table  20 gives nutrient  flux coefficients which might be  con-
sidered to  be  high,  low,  or  average values.  These values were
obtained by averaging  and comparing  available  coefficients
without regard to geographical  location.   Thus, the specification
of high or  low values  is  relative to  the other  numbers  in the
data  set, and  these  numbers  do  not  necessarily  apply  to  all
portions of the  country.   For example,  the average runoff coef-
ficient given  for dissolved inorganic phosphorus  from agricul-
tural  lands is 0.1 kg/ha/yr.  However,  for the  upper  Midwest,
it would be expected that the "average"  runoff  coefficient  would
be much  closer to 0.5  kg/ha/yr, the high value  listed in Table
 9.

It  is  apparent that nitrogen export from diffuse sources  is far
less  variable  than phosphorus runoff.   Ignoring land  use cate-
gories,  flux coefficients for total nitrogen vary  by  a factor
of  10,  and  soluble inorganic nitrogen values vary  by  a factor
 of  20.   In  comparison,  corresponding values for phosphorus  vary

                              107

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   Table  20.  TYPICAL  VALUES OF NUTRIENT RUNOFF COEFFICIENTS
NOa-N+NH^-N
kg/ha/yr
Land use
Urban
Forests
Agricultural
Hig
5.
3.
10.
jh
0
0
0
Low
1
0
1
Diss
.0
.5
.0
Ave
2.
1.
5.
0
6
0
High
10
5
10
.0
.0
.0
inorg-P
kg/ha/yr

Urban
Forests
Agricultural
Hig
2.
0.
0.
h
MM
0
1
5
"Low
0
0
0
.5
.01
.05
Ave
1.
0.
0.
0
05
1
Hi
^HBIBM
5
0
1
gh
.0
.8
.0
Total-N
kg/ha/yr
Low
2.5
1.0
2.0
Total-P
kg/ha/yr
Low
1.0
0.05
0.1


Ave
5.
2.
5.


0
5
0


Ave
1.
0.
0.
5
2
3
by factors of 100 and 200.  However, variation within land use
categories is smaller—nitrogen values vary by factors of about
5; phosphorus values vary by factors of 10.

The high and low runoff coefficients can be used to define ratios
of drainage basin area/lake area for which 1) permissible loading
levels would almost certainly be exceeded (low coefficient) and
2) ratios for which loadings would almost certainly be less than
permissible limits (high coefficients).  Using the same per-
missible loading levels as above—1.5 g-N/m2/yr and 0.1 g-P/m2/yr-
and considering only dissolved inorganic nutrient forms, this
approach yields the following extreme ratios of basin area/lake
area for which:
                              t-N loading would be:
                      below  limit        above  limit
  Urban
  Forests
  Agricultural
 3
 5
 1.5
 15
 30
 15
            Dissolved inorganic phosphorus loadings would be
                      below  limit         above  limit
  Urban
  Forests
  Agricultural
 0.5
10
 2
  2
100
 20
                             108

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  To place these values in perspective, basin area/lake area
  ratios for some of the larger lakes in Wisconsin are given in
  Table 21.  Of the 26 lakes listed, 6 had area ratios larger
  than 15, and 4 had area ratios less than 5.


 Table 21.  DIRECT DRAINAGE AREAS FOR SELECTED WISCONSIN LAKES3
Name
Impoundments:
  Mason L
  Arbutus
  L Wisconsin
  Beaverdam L
  Fox L
  Sinissippi
  St Croix
  Menomin
  Tainter
  Flambeau
  Gile Flow
  High Falls
  Buffalo
  Willow Flow
  Balsam L
  Chequamegon
County

Adams
Clark
Columbia
Dodge
Dodge
Dodge
Douglas
Dunn
Dunn
Iron
Iron
Marinette
Marquette
Oneida
Polk
Taylor
Lake area
    ha
Basin area
    km2
    347
    332
   3640
   2240
    858
    930
    774
    599
    709
   5481
   1369
    606
    990
   2078
    769
   1105
     60
     16
    319
    339
     98
    109
     41
     23
     65
    298
    137
     41
   1557
    246
    282
     44
  Basin area
  Lake area
(dimensionless)
       17
        5
        9
       15
       12
       12
        5
        4
        9
        5
       10
        7
      158
       16
       36
        4
Natural lakes :
Bear
Namekagon
Big Sand
L Mendota
Kegonsa
Waubesa
Kangaroo
Franklin
Big Green
^3
Bone

Barron
Bayfield
Burnett
Dane
Dane
Dane
Door
Forest
Green L
Polk

544
1298
567
3938
1099
855
445
361
2964
678

21
34
21
650
62
220
47
78
287
31

4
3
1 ,
4
17
6
26
10
22
10
5
  aBased on Wisconsin Department of Natural Resources
   lake inventory data.


   The potential significance of atmospheric contributions of both
   nitrogen and phosphorus were discussed previously.  In some
   parts of the United States, particularly in the Great Lakes
                                109

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 Region,  these  contributions may be large and, also, in
 situations where basin area/lake area ratios are small, bulk
 precipitation  may provide the majority of the nutrient input.

 Nutrient content of rainfall and dry fallout has been receiv-
 ing  a considerable amount of study during the past few years,
 and  additional study results are continually appearing in the
 literature.  The data listed here are rapidly becoming obso-
 lete and should be viewed as a summary of older studies.  An
 attempt  should be made to locate recent data applicable to the
 area in  question (particularly for phosphorus) before resorting
 to the data  listed in this report.

 Few  generalizations can be made regarding nutrient input to
 lakes via groundwater, other than to point out the highly
 variable nature of groundwater communication with lakes and
 the  potential  for sizable nutrient contributions—phosphorus
 as well  as nitrogen—in some situations.  At the present time,
 it appears that site-specific information is a necessity for
 estimating the  exchange of water between lakes and surrounding
 aquifers  and,  even when flow rates are known, the poorly-
 defined  role of bottom sediments as nutrient exchange media
 and  sites for  nutrient transformations greatly complicates
 estimation of nutrient influx.

 Hydrologic and chemical complexities of wetland areas have,
 for  the most part,  prevented the establishment of nutrient
 budgets for wetlands.   It appears that some wetland areas act
 like  "capacitors" which store nutrients for release at a later
 time  but, on an annual basis, there is no net storage or
 release of nutrients.   Until such time as the loading criteria
 for  lakes include consideration of the timing of nutrient
 inflow, flux coefficients for wetlands should probably be
 assumed to be zero.

 Considering the present state of knowledge, the estimation of
 nutrient loadings to lakes is as much an art as it is a science.
 The  selection of appropriate flux coefficients is critical;
 a wide range of values is possible; and guidelines to aid in
 the  selection of runoff coefficients are lacking.  Consequently,
 management decisions based on estimated loadings must be
 balanced against the inherent degree of uncertainty associated
with  the technique.   This uncertainty cannot be described in
 terms of an "accuracy of ± x%," but the limitations of the
 technique can be evaluated in a management context.

The  estimation of nutrient loadings is a logical first step
 in the development of almost any water quality management plan
                             110

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for lakes, because it forces the identification of potentially
significant nutrient sources and provides a measure of their
relative importance.  Based on this information, and in con-
sideration of practical constraints and opportunities which
exist, tentative management plans can be specified.  For
example, these plans might include a program of nutrient
abatement for the contributing watersheds.  At this point,
the adequacy of the estimated loadings can be evaluated.  If
the elements of the management plan are sensitive to the flux
coefficients used in the loading estimate, i.e., if the use
of slightly different flux coefficients would lead to the
conclusion that a different management approach should be
followed, then the limitations of the estimation technique
have been exceeded and site-specific field evaluation would
be necessary.  If not, it may be possible to rely on the esti-
mated loadings and eliminate, or at least reduce, the need for
extensive field monitoring and evaluation.

In all probability, the practice of estimating nutrient load-
ings of lakes will be expanded in the future.  The lack of
comparable alternatives almost assures that increased reliance
will be placed on this approach.  The technique has limita-
tions which must be recognized but, despite its shortcomings,
it can be a valuable decision-making tool.
REFERENCE


Armstrong, D.  E. ,  K.  W.  Lee,   P.  D.  Uttormark,  D.  R. Keeney,
     and R.  F.  Harris.   197M-.   Pollution of  the Great  Lakes
     by Nutrients  from Agricultural  Land.  Great Lakes Basin
     Commission, Ann  Arbor,  Mich.   96  p.
                              Ill

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Table 12.  CONVERSION FACTORS
acres x 0.405 =
mi2 x 259 =
m2 x 10-4*
km2 x 100
Ibs x 0.454
ton x 907.2 =
Ibs/acre x 1.12 =
ton/mi2 x 3.5 =
ton/acre x 2242 =
Ibs/mi x 0.00176 =
acre- ft x 1233.5 =
ha
ha
ha
ha
kg
kg
kg/ha
kg/ha
kg/ha
kg/ha
m3
x 2.471
x 0.00386
x 101*
x .01
x 2.205
x .0011
x 0. 892
x 0.286
x 0.000446
x 569. 8
x 0.00081
= acres
• 9
= miz
= m2
= km2
= Ibs
= ton
= Ibs/acre
= ton/mi2
= ton/acre
= Ibs /mi
= acre- ft
             112

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SELECTED WATER
RESOURCES ABSTRACTS
INPUT TRANSACTION FORM
                                              1.  Report No.
                                                                   }.  Accession No.
                                                    w
 4. Title
         ESTIMATING NUTRIENT LOADINGS  OF LAKES FROM NON-POINT
    SOURCES,
 7. Aulhor(s)
    Uttormark, P. D., Chapin, J.  D.,  and Green, K. M.
    Wisconsin Univ., Madison.   Water Resources Center.
                                                     5. Report Date

                                                     6
                                                     3. Performing Organization
                                                       Report >
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