United States
Environmental Protection
Agency
EPA-90D-79-006 B
Applicability of Land
Treatment of
Wastewater in the Great
Lakes Area Basin
Effectiveness of Sandy
Soils at Muskegon County,
Michigan, for Renovating
Wastewater
MCD-55
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Preface
The U. S. Environmental Protection Agency was created because of in-
creasing public and governmental concern about the dangers of pollu-
tion to the health and welfare of the American people. Noxious air,
foul water, and spoiled land are tragic testimony to the deterioration
of our natural environment.
The Great Lakes National Program Office (GLNPO) of the U.S. EPA was
established in Region V, Chicago, to provide specific focus on the
water quality concerns of the Great Lakes. The Section 108(a)
Demonstration Grant Program of the Clean Water Act (PL92-500) is
specific to the Great Lakes drainage basin and thus is administered
by the Great Lakes National Program Office.
Land disposal of wastewater in the Great Lakes area is one alternative
for treatment that can provide tertiary quality effluent when properly
managed. This report evaluates the effectiveness of sandy soils at
Muskegon County, Michigan, for renovating wastewater.
We hope the information and data contained herein will help planners and
managers of pollution control agencies to make better decisions
in carrying forward their pollution control responsibilities.
Edith J. Tebo, Ph.D.
Director
Great Lakes National Program Office
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APPLICABILITY OF LAND TREATMENT OF WASTEWATER
IN THE GREAT LAKES AREA BASIN:
EFFECTIVENESS OF SANDY SOILS AT NUSKEGON COUNTY,
MICHIGAN, FOR RENOVATING WASTEWATER
by
B. G. Ellis, A. E. Erickson, A. R. Wolcott, B. D. Knezek,
J. M. Tiedje and J. Butcher
Departments: Crop and Soil Sciences, Entomology
Michigan State University
East Lansing, Michigan 48824
for
Michigan Water Resources Commission
Department of Natural Resources
Lansing, Michigan 48926
EPA Grant No. G005104
Project Officers
J. M. Walker and S. Poloncsik
Office of Research and Development
SECTION 108 (a) PROGRAM
GREAT LAKES NATIONAL PROGRAM OFFICE
U.S. ENVIRONMENTAL PROTECTION AGENCY, REGION V
CHICAGO, ILLINOIS 60605
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EPA REVIEW NOTICE
This report has been reviewed by the Office of Research and Development
and the Great Lakes National Program Office of Region V, U.S. EPA,
Chicago, and approved for publication. Approval does not signify that
the contents necessarily reflect the views and policies of the Environmental
Protection Agency, nor does mention of trade names or commercial products
constitute endorsement or recommendation for use.
ii
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FOREWORD
The Great Lakes are the world's largest fresh water resource. It is
shared by the United States and Canada. In the U.S., this lake system
serves important water needs of people and industries in eight states,
six of which comprise the area served by EPA Region V. The usefulness
of the lakes, for many purposes, has been impaired by past misuses of
the lakes themselves and of land resources in contributing drainage
basins. Management of the Great Lakes Area Basin to halt or reverse the
degradation of vital water resources is of great importance to both
countries. Lake Michigan presents special concerns because of its
headwater relationship to the lower Great Lakes and because of the
intensity and variety of human activity that impacts upon it. Responsi-
bilities for developing and enforcing ameliorative management in the
Lake Michigan basin rest with the U.S. and the four states that share
the shoreline of the lake.
Land application of wastewater is one of the management options for
upgrading water after use. From historical precedent and for many
theoretical reasons, land application has the potential for effecting
full renovation of wastewater before release into the environment.
Whether this potential is realized will depend on many factors of soil,
climate and management which must be understood for each situation.
Performance must be assessed ultimately in terms of impact on contiguous
aquatic systems. The acquisition of background and early operational
data for a large land application system in Muskegon County, Michigan,
has been the objective of an intensive three-year study conducted for
EPA Region V by the Michigan Water Resources Commission, with sub-
contracts to Michigan State University and the University of Michigan.
The three reports covering this work carry the general title, "Applicability
of Land Treatment of Wastewater in the Great Lakes Area Basin," with
respective subtitles:
The Muskegon County System—An Overview, Monitoring Considerations
and Impacts on Receiving Waters.
Effectiveness of Sandy Soils at Muskegon County, Michigan, for
Renovating Wastewater.
Impact of Wastewater Diversion, Spray Irrigation on Water Quality
in Muskegon County, Michigan, Lakes.
In these volumes, data collected from 1972 through 1975 are evaluated in
relation to the applicability of land treatment for renovating municipal
and industrial wastewaters in Muskegon County. Short-term and long-term
projections are made regarding management practices that can influence
the renovative effectiveness of soils and crops. Observed and projected
effects of wastewater diversion and treatment on water quality and
ecosystem responses in lakes and streams that drain into Lake Michigan
are described.
iii
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ABSTRACT
A key concept in design of the Muskegon Wastewater Management System is the
use of soils and crops as a "living filter." Management to achieve a desired
degree of renovation at acceptable cost requires a knowledge of changes that
occur in water as it passes through the system, as well as a knowledge of
changes in soil that can be projected to estimate useful life of the system.
Four major soil types (Rubicon sand, AuGres sand, Roscommon sand and Granby
loamy sand) comprise a majority of the land area on the Muskegon wastewater
management site. Analysis of soil profile samples representing each of the
four major soil types were conducted to determine the level of Kjeldahl N, N0_,
NH4, Ca, Mg, Na, K, P, Fe, Zn, Mn, Cu, Hg, Pb, total C and pH prior to appli-
cation of wastewater and after application of wastewater during 1974 and 1975.
Summaries of data are given in this report. Some nitrate moved through the soil
profiles, apparently more the result of initiating the farming operation than
from applying wastewater. Phosphorus was being adsorbed by the Rubicon sands
and Roscommon sands. The AuGres sands did not appear to be adsorbing P, and
insufficient wastewater had been applied to the Granby loamy sands to make a
valid inference. Soils which had received more than 300 cm of wastewater had
reached an equilibrium with respect to Na, Ca and Mg which allowed most of the
Na applied to pass through the soil profile. Soil pH was increasing and should
approach the pH of the wastewater in a few years. There was no apparent accumu-
lation of heavy metals in the soils due to a very low input of metals.
Soil physical properties were evaluated by measurement of infiltration rate,
hydraulic conductivity and bulk density. The majority of these very sandy
soils will conduct water so fast that infiltration and hydraulic conductivity
should not be a problem. However, a small percentage of the soils mapped as
Saugatuck or AuGres have been observed to have very slow hydraulic conductiv-
ities.
Electron-capturing organic chemical species were monitored in soils and waters,
using multi-column gas-liquid chromatography and thin layer. Patterns of
encounter with 26 pesticide parameters in incoming wastewater are evidence
that chemicals from non-point sources can enter through feedwaters taken from
lakes and streams by industries that discharge into the system. By inference,
chemicals that originate in extramural point-source discharges can enter also.
The potential problem from industrial trace organics originating within the
service area was addressed only superficially by analytical protocol employed
in this study. Evidence was obtained for chronic entry, at substantial con-
centrations, of diethylhexylphthalate and three unreferenced electron-capturing
species. Removals of trace organics from wastewater occurred in storage lagoons
and during passage through the soil mantle. Chromatographic peaks observed in
incoming wastewater and peaks for pesticides used on site were found in extracts
of soils sampled after the system was placed in operation. Intercepted chemicals
were found mainly in surface and shallow subsoil layers. Organic chemicals
detected in drainage at outfalls were associated with heavy rains and with
IV
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seasonally heavy applications of wastewater on restricted soil areas.
Frequency and concentration at outfalls for chronically input chemicals
declined from 1974 to 1975. This suggests developmental changes in lagoons
and soils leading to increased effectiveness in removal of these chemicals
from wastewaters passing through the system.
This report was submitted in fulfillment of a subcontract by Michigan State
University to Michigan Water Resources Commission as part of their Grant
No. G005104 under the sponsorship of the U.S. Environmental Protection
Agency. This report covers the period of April 1, 1972 to December 31, 1975,
and work was completed as of June 30, 1976.
v
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CONTENTS
Page
Forward ill
Abstract iv
List of Figures ix
List of Tables x
Abbreviations xv
Acknowledgements xvi
Sections
I Summary and Conclusions 1
II Recommendations 7
III Introduction 9
IV Chemical Analysis of Soil Profile Samples 16
Introduction 16
Nitrogen 18
Effect of Soil Type on the Initial Nitrogen Content of
Soil Profiles 18
Effect of Drainage and Farming on Nitrogen in Soil
Profiles 28
Effect of Application of Wastewater on Nitrogen Distri-
bution in Soil Profiles 30
Calcium, Magnesium, Sodium, and Sodium Adsorption Ratio (SAR^ 36
Cation Exchange Capacity 38
Background Levels of Exchangeable Bases 38
Changes in Exchangeable Bases with Application of
Wastewater 39
Phosphorus 42
Effect of Soil Type on the Initial Phosphorus Content of
Soil Profiles 42
Phosphorus Adsorption Maximum for the Major Soil Types . 42
The Relationship between Phosphorus and Agricultural
Production 44
Phosphorus Adsorption by Soils after Application of
Wastewater 44
Life of Site for Phosphate Removal 48
Soil pH 51
Background data 51
Changes Induced by Agronomic Development 52
Changes Induced by Wastewater Application 52
Total Carbon 52
Postassium 53
Background Data for Potassium 53
Changes Induced by Wastewater Application 53
vi
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CONTENTS (Continued) ^
Page
Total Soil Analysis 55
V Heavy Metals 57
General Background and Summary 57
Chelate Extractable Heavy Metals 67
VI Soil Physical Properties 68
Study Sites 68
Methods of Study 68
Infiltration 68
Mechanical Composition 69
Hydraulic Conductivity and Soil Water Characteristic . 69
Aeration and Redox 70
Results and Discussion 70
Mechanical Composition 70
Soil Water Characteristics, Bulk Density and Hydraulic
Conductivity 70
Infiltration 72
Oxygen Diffusion Rates and Redox Potential 72
Addendum 72
VII Microbial Studies 74
VIII Pesticides and Industrial Trace Organics 77
Introduction 77
Procedures 78
Sampling and Extraction of Soils 78
Sampling and Extraction of Water 79
Cleanup of Extracts 79
Detection and Quantitation of Organics 79
Confirmation of Peak Identities 79
Trace Organics in Waters 79
Probable Sources and Modes of Entry 80
Raw Influent and Discharges into Storage 84
Pre-Chlorination Flows and Irrigation Water (1974) . .106
Outfall Waters 106
Frequencies of Occurrence and Ranges of Concentration
in Waters 110
Particulate-Phase/Aqueous Phase Distributions 113
Trace Organics in Soils 115
Background Samples 115
Post-Irrigation Samples 126
Frequencies of Occurrence and Ranges of Detection. . .127
Evaluation of Methods 134
Summary—Trace Organics 137
Recommendations 138
Research Needs 139
References 141
Appendix I—Methods of Analysis for Nutrients 145
Appendix II—Analytical Procedures for Trace Organics 150
Appendix III--Nutrient Content of Corn 164
vii
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CONTENTS (Continued)
Appendix IV--Availability of Data From U.S. EPA Storage
and Retrieval Computer System "STORET" 165
Vlll
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FIGURES
Number Page
1 Location of sampling sites for soils and outfalls . . .15
2 Major soil types at Muskegon Wastewater Treatment site. . .17
ix
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TABLES
Number Page
1 List of Chemical Analyses Data Reported During Project
Period 12
2 Wastewater Application to Sampling Sites 13
3. Estimation of the Quantity of Nutrients Applied to Soils
through Irrigation with Wastewater 14
4 Sites Combined in Summarizing Each Soil Type 19
5 Mean and Standard Deviations for Extractable and soluble
Nutrient Content of Soils from Muskegon Spray Area-
Baseline Data Rubicon Sand 20
6 Mean and Standard Deviations for Extractable and Soluble
Nutrient Content of Soils from Muskegon Spray Area-
Baseline Data Roscommon Sand 21
7 Mean and Standard Deviations for Extractable and Soluble
Nutrient Content of Soils from Muskegon Spray area-
Baseline Data Augres Sand 22
8 Mean and Standard Deviations for Extractable and Soluble
Nutrient Content of Soils from Muskegon Spray Area-
Baseline Data Granby Sand 23
9 Mean and Standard Deviation for total Nutrients of Soils
from Muskegon Spray Area-Baseline Data Rubicon Sand. 24
10 Mean and Standard Deviation for Total Nutrients of Soils
from Muskegon Spray Area-Baseline Data Roscommon Sand 25
11 Mean and Standard Deviation of Total Nutrients of Soils
from Muskegon Spray Area-Baseline Data Augres Sand. .26
12 Mean and Standard Deviation of Total Nutrients of Soils
from Muskegon Spray Area-Baseline Data Granby Sand. .27
13 Ammonium and Nitrate Contents of the Soil Profile at Site
35 (Granby Sand) 29
14 Mean and Standard Deviations for Extractable and Soluble
Nutrient Content of Soils from Muskegon Spray Area
After Eight Inches of Effluent Rubicon Sand 31
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TABLES (Continued)
Number Page
15 Mean and Standard Deviations for Extractable and Soluble
Nutrient Content of Soils from Muskegon Spray Area
After Eight Inches of Effluent Roscommon Sand 32
16 Mean and Standard Deviation for Extractable and Soluble
Nutrient Content of Soils from Muskegon Spray Area
After Eight Inches of Effluent AuGres Sand 33
17 Mean and Standard Deviation for Extractable and Soluble
Nutrient Content of Soils from Muskegon Spray Area
After Eight Inches of Effluent Granby Sand 34
18 Ammonium Content of Soil From Site 01. (Circle 5) as
Compared to the Average of the Remaining Seven Rubicon
Sites 35
19 Average Content of Wastewater in the Lagoons at Muskegon
waste Treatment Facility (Data from Demirjian, 1975,
1976) 37
20 Sodium, Calcium and Magnesium Concentrations in the Soil
Profile of Site 01 (Circle 5) as a Function of Effluent
Application 40
21 Phosphorus Adsorption Capacity of Selected Samples from
Muskegon Wastewater Facility 43
22 Increase in Extractable P after Application of 380 cm
Wastewater to Site 02 (Circle 8) 46
23 Change in Extractable P After Application of 380 cm
Wastewater to Site 04 (Circle 24) 47
24 Estimated Number of Years that P may be Removed from Waste-
water Applied at 152 CM (60 Inches) per year 49
25 Effect of Uneven Distribution of Water on the Effective
Life of P Removal on Rubicon Sand 50
26 Ammonium Acetate Extractable K at Various Sampling Periods. 54
27 Mean and Standard Deviation of Extractable Heavy Metals of
Soils from Muskegon Spray Area-Baseline Data Rubicon
Sand 58
28 Mean and Standard Deviation of Extractable Heavy Metals of
Soils from Muskegon Spray Area-Baseline Data Roscommon
Sand 59
xi
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TABLES (Continued)
Number Page
29 Mean and Standard Deviation of Extractable Heavy Metals of
Soils from Muskegon Spray Area-Baseline Data AuGres ... 60
30 Mean and Standard Deviation of Extractable Heavy Metals of
Soils from Muskegon Spray Area-Baseline Data Granby Sand. 61
31 Mean and Standard Deviation of Total Heavy Metals of Soils
from Muskegon Spray Area-Baseline Data Rubicon Sand ... 62
32 Mean and Standard Deviation of Total Heavy Metals of Soils
from Muskegon Spray Area-Baseline Data Roscommon Sand . . 63
33 Mean and Standard Deviation of Total Heavy Metals of Soils
from Muskegon Spray Area-Baseline Data AuGres Sand. ... 64
34 Mean and Standard Deviation of Total Heavy Metals of Soils
from Muskegon Spray Area-Baseline Data Granby Sand.... 65
35 Changes in Chelate Extractable Fe, Mn, Zn and Cu after Appli-
cation of Wastewater 66
36 Summary of Averages of Soil Physical Properties by Soil Series
and Horizons 71
37 Summary of Infiltration Rates Determined During 1973-1975. . 73
38 Change in Microbial Populations and Selected Chemical Parameters
in Response to Initial Wastewater Irrigation on Three
Soil Types 75
39 Trace Organics in Raw Influent, Muskegon, December 1973 to
December 1974 85
40 Trace Organics in Raw Influent, Muskegon, Jan to Dec 1975. . 86
41 Trace Organics in Discharges into Storage Lagoons, Muskegon,
April to Dec. 1974 87
42 Trace Organics in Discharges into Storage Lagoons, Muskegon,
Jan. to Dec. 1975 88
43 Trace Organics in Raw Influent and in Discharge into Storage
Whitehall, Apr. to Dec. 1975 89
44 Trace Organics in Pre-Chlorination Flows and Irrigation Water,
Muskegon, Jun. 74 to Dec. 74 90
45 Trace Organics in North Outfall Waters (SW-05, Mosquito Creek),
Muskegon; Apr. 74 to Dec. 75 91
xii
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TABLES (Continued)
Number Page
46 Trace Organics in South Outfall Waters (SW-34, Black
Creek), Muskegon, Apr. 74 to Dec. 75 92
47 Frequencies of Occurrence, Trace Organics in Waters, Muske-
gon, Dec. 73 to Dec. 75 93
48 Detected Ranges of Concentration, Trace Organics in Water,
Muskegon, Dec 73 to Dec. 75 94
49 Distribution of Trace organics Between Particulate and
Aqueous Phases, Muskegon Wastewaters, Dec. 73 to Dec 75.114
50 Trace Organics in Soils, Muskegon and Whitehall Systems,
Background Samples Taken Summer 1972 or June 1973 (25
Surface Samples, 14 Subsoil Samples) 116
51 Trace Organics in Soils, Special Study Sites, Muskegon,
Background Samples Taken June 197 3 and April 1974 (Sur-
face Soils, 0-6") 119
52 Trace Organics in Soils, Special Study Sites, Muskegon,
Background Samples Taken June 1973 and April 1974 (Sub-
Soils, 46-61 cm) 120
53 Trace Organics in Soils, Special Study Sites, Muskegon,
(November 1974 Sampling) 121
54 Trace Organics in Soils, Special Study Sites, Muskegon
(April 1975 Sampling) 122
55 Trace Organics in Soils, Special Study Sites, Muskegon
(October 1975 Sampling) 123
56 Trace Organics in Soils, Special Study Sites, Whitehall,
Background Samples Taken June 1973 and April 1974. . . 124
57 Trace Organics in Soils, Special Study Sites, Whitehall,
(Samplings of Nov. 1974, Apr. 1975 and Oct. 1975). . . 125
58 Frequencies of Occurrence, Trace Organics in Soils, Muskegon,
June 73 to October 75 128
59 Frequencies of Occurrence, Trace Organics in Soils, Whitehall,
June 73 to October 75 129
60 Detected Ranges of Concentration. Trace Organics in Soils,
Muskegon, June 73 to Oct. 75 130
61 Detected Ranges of Concentration, Trace Organics in Soils,
Whitehall, June 73 to October 75 .131
xiii
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TABLES (Continued)
Number Page
II-l Reference Chemicals (Purified Grade) and Sources .... 159
II-2 Standard Solutions in (Benzene): Retention Times (R )
on Four GLC Columns and Typical Sensitivities and
Detection Limits for the Quantitating Column 161
II-3 Florisil Eluants: Fractional Distributions and Total
Recoveries for Reference Chemicals 163
III-l Estimated Nutrient Content of Corn Grain (15.5% Moisture)164
xiv
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LIST OF ABBREVIATIONS AND SYMBOLS
ABBREVIATIONS
X
SD
ppm —
ppb
me —
ml —
cm —
8
kg/ha
ng/g
ng/1
GLC
TLC
GC-MS
BCD
SYMBOLS
mean
standard deviation
parts per million
parts per billion
milliequivalent
milliliter
centimeter
gram
kilogram/hectare
nanograms/gram (ppb)
nanograms/liter (parts per trillion)
gas-liquid chromatography
thin layer chromatography
mass spectrographic analysis of chemical species
isolated by preparative gas chromatography
electron capture detector
N
P
K
Ca
Mg
Na
Zn
Cu
Mn
Fe
Pb
Hg
Cr
NH4H
N03'
nitrogen
phosphorus
potassium
calcium
magnesium
sodium
zinc
copper
manganese
iron
lead
mercury
chromium
carbon
ammonium ion
nitrate ion
xv
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ACKNOWLEDGMENTS
We gratefully acknowledge the cooperation and effort made by many
individuals in the development and operation of this project. In
particular, Dr. Demirjian and his staff and the County of Muskegon
have been most cooperative and helpful in allowing us to collect
samples, collecting and retaining samples for us, and lending assis-
tance and equipment for on-the-spot use. Their data has also been
made available whenever requested and has been absolutely necessary
for the interpretation of our data.
The Michigan Water Resources personnel have also contributed greatly
to the project in discussions and assembling and reproducing reports.
We would also gratefully acknowledge the cooperation and guidance
of Stephen Poloncsik and Dr. John M. Walker, Project Officers during
various phases of this project; Mr. Robert Bastian, EPA's special
representative at Muskegon; and to the Region Five personnel, Mr.
Ralph G. Christenson and Mr. Cliff Risley who worked closely with
the project.
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SECTION I
SUMMARY AID CONCLUSIONS
GENERAL
Baseline data has been established for the major soil types at the Muskegon
land treatment system (Rubicon sand, Roscommon sand, AuGres sand, and Granby
loamy sand) for physical properties, chemical analysis, heavy metals, pesti-
cides, and certain industrial organics, microorganisms, and arthropods.
Establishment of the baseline levels and the soil variability within the soil
irrigation site allows for evaluation of the effectiveness of the land treat-
ment process in renovating wastewater. Comparisons between baseline data and
soil analysis after one or two years of application of wastewater will allow
for predictions of the effectiveness of the system and possible management
changes that must be made to improve the effectiveness of the operation.
The soils were initially free of contamination from heavy metals. Very low
levels of dieldrin and DDT species were indicated in most surface soils and
many subsoils, using chromatographic methods and electron capture for de-
tection.
CHEMICAL ANALYSIS
Both total and "available" nutrient analyses were determined for P, K, Ca,
Mg, and Na on profile samples from each of the major soil types. Profile
samples were collected twice yearly from 15 cm (6 inch) layers to depths of
305 cm (10 feat). Total C and N, distillable NH3, soluble N03, and pH were
also determined. From the data the following conclusions were drawn:
1. Available or extractable nutrients are much more sensitive to changes
produced by wastewater application for P, K, Ca, Mg, and Na than is total
analysis. Changes in the available fraction were detected after as little
as 20 cm (8 inches) of wastewater application; whereas, few differences were
noted in total analysis after application of more than 380 cm (150 inches)
of wastewater.
2. The NO^ content of Rubicon, Roscommon, and AuGres sands is low. Further-
more, irrigation with the rather low N containing wastewater does not supply
adequate N for maximum growth of corn during the period of peak demand (i.e.,
during the months of July and August), but during the remainder of the year
some N as N03 is expected to be lost through the soil into the drainage water
because it is present in excess of crop needs. In general, this quantity of
N moving in the soil profiles was under 5 ppm N as NO^, but occasional samples
were much higher. The NO^ tended to move in bands in the soil profiles. High
values for N03 were raore comnonly found in the Granby soils and appeared to
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originate from the oxidation of native organic matter in the surface layers
and not from wastewater application.
3. Phosphorus was effectively removed from the wastewater applied to
Rubicon sand by adsorption in the surface layers. The effective life of
the Rubicon sand for removal of P by this mechanism should be more than 50
years at the present level of P input (less than 3 ppm P), average applica-
tions of 150 cm water per year, and with yields from 80 to 100 bushels of
corn per acre. Initial data did not show a gain of P in the AuGres and Gran-
by soils. This may be partially attributed to lower application rates, par-
ticularly for the Granby soils, but adsorption isotherms also indicated that
these soils had lower adsorption capacities and that the AuGres soils may not
bind P as tightly as the other soil series.
4. Uneven distribution of wastewater on the soil may adversely affect the
life of the system. One site appeared to have received far less water in the
sampling area than was reported which suggests heavier application in other
parts of the circle. This can lead to P leaking at an earlier than predicted
time.
5. Two years of application of wastewater was adequate to allow for passage
of Na throughout the profile. A land treatment system is not effective in
removing cations (Na, Ca, Mg and K), but rather the process that functions
is one of cation exchange whereby adsorption of one base will result in re-
lease of another. Some adsorption of Na does occur in the soils with release
of Ca, but an equilibrium is soon reached after which the water passing
through the soil will be very similar in bases to the wastewater being ap-
plied. Our data would suggest that on all sites where greater than 305 cm
(120 inches) of wastewater have been applied, the Wa content of the tile
drainage water should be the same as the water being applied. Where dis-
charge water levels of Na are lower than in the wastewater, dilution by
other drainage water has apparently occurred. The level of exchangeable Na
at this equilibrium is not expected to cause appreciable change in the physi-
cal properties of these very sandy soils. High levels of Na in soils may lead
to dispersion of clay and organic matter and reduced infiltration of water.
Rubicon, Roscommon and AuGres sands are so low in clay and organic matter
content that they are unlikely to be affected by the levels of Na in the
wastewater. If any changes do occur, they should be expected on the Granby
soil which is considerably higher in organic matter. Insufficient water has
been applied to the Granby soils at this time to ascertain if there will be
any dispersion effects in the soil resulting in decreased ability of the soil
to accept water.
6. Potassium is moving through the soils and leaching into the discharge
waters. This occurs because the concentration of K is much lower in the
water being applied than is the concentration of Ca and Mg and does not com-
pete favorably with Ca and Mg for exchange sites. In addition to concentra-
tion, a major factor is that the monovalent K ion is not bonded as strongly
to the exchange complex as are the divalent Ca and Mg ions.
7. Total C content of Rubicon, AuGres and Roscommon soils is very low.
Hence, these soils are very effective in eliminating BOD from the applied
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wastewater. An increase in organic matter (C) would likely increase the
agricultural productivity of these soils. This could be accomplished
through application of sludge. Since the Granby soils are already high in
total C in the surface layers, low in P adsorption capacity, and release N
by decomposition of organic matter, an application of sludge would not be de-
sirable, but if well drained, the Granby soils will function well in reducing
BOD from wastewaters.
8. Soil pH is increasing rapidly with the application of wastewater and
should stabilize within the next two years to a level near that of the in-
coming wastewater. The soil adsorbs Ca, Mg and Na from the wastewater and
the H replaced is neutralized by the basic water. This pH is slightly higher
than is desirable for agronomic purposes but should pose little problem.
9. Low soil pH's resulted from draining and aerating the Granby soils prior
to application of wastewater. This is usually a result of oxidation of S
that has accumulated in the subsoils. As a result, Fe was mobilized and
moved into the drainage watar. These soil pH values are increasing due to
movement of bases down in the profile after application of wastewater and to
soil chemical reactions. Iron in the soil should soon stabilize as the pH
increases above 4 to 5.
PHYSICAL MEASUREMENTS
Initial clearing and beginning farming operation of these soils has left them
so variable in the surface layers that meaningful physical measurements are
difficult, and it is impossible to establish trends from the short period of
time that wastewater has been applied. But the following conclusions may be
drawn:
1. Infiltration rates are so high on all major soil types that it is diffi-
cult to imagine that this will ever become a limiting factor. But some micro-
areas of Saugatuck sand may have limited infiltration.
2. All aeration measurements have shown a high degree of aeration except
where there are definite drainage malfunctions. Therefore, once drainage is
improved, aeration should be no problem.
HEAVY METALS
Selected total and chelate extractable micronutrient and heavy metal analyses
were conducted on soil profile samples. The elements determined were Fe, Mn,
Zn, Cu, Pb, and Hg on samples taken at 15 cm (6 inch) intervals down to a
depth of 305 cm (120 inches) in Rubicon sand, Roscommon sand, AuGres sand,
and Granby loamy sand which are the main soil types on the wastewater treat-
ment site. From the data, the following conclusions were drawn:
1. Total analyses indicate that none of the soil metals were increased sig-
nificantly by the addition of wastewater. Lead and Hg, which are of parti-
cular concern, are still at levels below the detection limits of the methods
used. Zinc which may have been added in amounts up to 0.2 ppm Zn in the
wastewater, did not show any total accumulation, even though 7.8 kg/ha of Zn
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per acre could have been added at sites receiving more than 380 cm (150 in-
ches) of wastewater. Crop removal would account for less than 1 kg/ha of Zn.
Therefore, Zn should be detected in the surface samples in the next few years
if the level in the irrigation water is greater than 0.1 ppm Zn.
2. Total Fe values fluctuated considerably throughout the soil profile, but
there was no obvious change in Fe content with profile depth. Total Cu and
Zn, and to a lesser extent Mn, were localized in the top 15 cm (6 inches) to
30 cm (12 inches) of soil. The initial concentrations appeared to be asso-
ciated with the organic matter in the surface layer of the soil. After
plowing, the total Cu, Zn, and Mn were distributed to the depth of the plow
layer, but they did not move by leaching below that point over the duration
of the study. The total quantity of heavy metals applied in wastewater (380
cm) was very small compared to the total initially in the soil (less than 0.1
percent in all cases). The localization of total Cu, Zn, and Mn in the sur-
face layers was most pronounced in the Rubicon sand. By contrast, the total
Mn was relatively evenly distributed throughout the soil profile of the Gran-
by soil. The other soils fell between these extremes. The Mn in the lower
profile of the Granby sand can be explained by the relatively flooded (re-
ducing) conditions in the soil prior to drainage. The flooded conditions
favored the formation of the relatively soluble manganous ion (Mn"*~^) which
could move through the soil profile. In contrast, conditions in the well-
aerated Rubicon sand favored the formation of the manganic ion (Mn+^) which
forms relatively insoluble oxides that cannot move in the soil profile. Also,
much of the Mn appeared to be associated with and bound to soil organic matter,
and Rubicon sand contained little organic matter below the soil surface.
Since solubility of Cu and Zn are not significantly influenced by soil oxida-
tion-reduction status, there were no pronounced changes in their soil profile
distributions as the result of aeration status.
3. Chelate extractable soil micronutrients were determined to estimate the
magnitude of an "available" fraction which is potentially available for plant
uptake and to movement through the soil profile with irrigation water. The
relative degree of extractability closely paralleled the total amount of
micronutrient in the soil profile. The relative magnitude of extractability
was as follows: Fe>Mn>Zn>Cu. Iron and Mn were the micronutrients most in-
fluenced during the time frame of the investigation. The changes which were
observed were due to changing the oxidation status of the soil with soil water
drainage and to disturbing the surface soil organic matter layer with the be-
ginning of cultivation practices. Generally, the amount of extractable Fe
and Mn was high in the surface layers of the soil initially and decreased as
the organic fraction was broken up with cultivation practices. Extractable
Fe in the surface layers decreased from a range of 50 to 200+ ppm Fe ini-
tially to 10 to 40 ppm Fe by the seventh sampling. Initially there were some
relatively high amounts of extractable Fe (as much as 40 ppm Fe) in the lower
levels of the soil profiles which had been flooded. However, as these soils
were drained, the extractable Fe decreased to a background level below 10 ppm
Fe due to leaching of soluble Fe and formation of ferric hydroxide in the
well-aerated conditions.
Extractable Mn initially ranged from 1 to 40 ppm Mn in the surface layers.
The extractable Mn levels below the surface layers dropped to about 1 ppm Mn
-------
and continued to decrease with time. Most of the extractable fraction was
associated with the organic matter in the soil, and as the soil became well
aerated, less Mn was extractable due to the formation of more insoluble
manganese oxides.
Extractable Cu and Zn were less influenced by effects of management changes
on the soil.
TRACE ORGANICS
Local and regional hydrologic systems were described in some detail, with a
view to identifying probable sources and modes of entry for trace organics
into wastewater collection systems at Muskegon and Whitehall. Electron-cap-
turing species were monitored in monthly composites of incoming wastewater
and outfall drainage over a two-year period. The same analyses were per-
formed on extracts of soils sampled biennially, twice before and three times
after wastewater irrigation was initiated at the treatment sites. Implica-
tions and limitations of the data are summarized here:
1. Patterns of encounter with 26 pesticide parameters provide evidence that
chemicals from non-point sources can enter these systems through connected
discharges from industries that take their feedwaters from Muskegon Lake,
Mona Lake, White Lake or tributary streams. By inference, chemicals origin-
ating at extramural point-sources can be expected also.
2. A wide range of industrial chemicals which have become the focus of con-
cern in these systems was not addressed by analytical methods used in this
study. Credible evidence for chronic entry of DEHP was obtained. Peaks for
several unreferenced electron-capturing species were present frequently in
incoming wastewater but were not identified.
3. In background soil samples, dieldrin and DDT species were indicated at
the very low concentrations that might be expected from global circulation,
with evidence at one sampling station for locally higher residues from earlier
use.
4. Chromatographic peaks observed in incoming wastewaters and peaks for pes-
ticides used on site were found in extracts of soils after the systems were
placed in operation in 1974. Both referenced and unreferenced species were
found mainly in surface (0-15 cm) and shallow subsurface layers (46-61 cm).
Encounters at 91-107 cm were infrequent or at levels approaching the limit
for quantitation.
5. Outfalls were monitored only at the Muskegon site. Detectable
amounts observed for a number of chemicals were associated with heavy
rains or with seasonally expedient modes of operation that resulted in un-
usually heavy applications of wastewater on limited soil areas.
6. Data for successive flow points at Muskegon indicate that removals of
trace organics occurred both in storage lagoons and during passage through
the soil mantle. Chemicals intercepted most effectively were those that are
strongly adsorbed by soils or sediments and those that are readily metabo-
-------
lized. Chemicals responsible for unreferenced GLC/ECD peaks appeared to be
more recalcitrant or more mobile in soils than the referenced species.
7. Chemicals observed frequently in incoming wastewater (lindane, heptachlor,
related species, DEHP) declined in frequency and concentration at outfalls
from 1974 to 1975. This is hopeful evidence that the efficiency of the
system in removing exotic chemicals may improve over time. Beneficial devel-
opmental changes may include the induction of adaptive enzymes in lagoons and
soils, increasing volume and adsorptive surface of sediments in lagoons, and
increased annual return of crop residues and exudates to support cometabolism
of recalcitrant compounds in soils and residual increases in adsorptive soil
organic matter.
MICROBIAL STUDIES
Limited microbial studies were made on three soil types representing the ex-
tremes in the Muskegon land treatment site before and after wastewater appli-
cation. The populations analyzed for were nitrifiers, denitrifiers, aerobes,
and anaerobes. The following conclusions were drawn:
1. There was initially a very low number of nitrifiers on the Rubicon and
AuGres sands probably due to the very low soil pH. This also related to
higher ammonium values on these soils. As the pH increased with wastewater
application, the numbers of nitrifiers increased and ammonium disappeared.
The Granby initially had high soil pH's and a high nitrifier population.
2. The denitrifier population relative to the total aerobes and anaerobes
was quite low in all soils, but there was a slight increase with irrigation,
particularly in the Rubicon soil.
3. Irrigation with wastewater had no detrimental effect on the soil micro-
bial community.
SOIL ARTHROPOD STUDY
Samples of soil arthropods were obtained and studied from each of the four
major soil types. The soil animals were extracted and sorted into major
groups. The soil faunal categories found to occur in the study area were:
Diptera, Diptera larvae, Coleoptera larvae, Hemiptera, Thysanoptera,
Enchytraeidae, Nematoda, Oribatid mites, predatory mites, and Collembola.
The major conclusion is that the site was and is very poor in both number
of species and in number of individuals. If the soil organic fraction in-
creased through application of sludge, the arthropod population would be
expected to increase.
-------
SECTION II
RECOMMENDATIONS
GENERAL
Soil monitoring information indicates that the Muskegon County land treatment
site is generally operating in a satisfactory manner. The initial years'
study indicates that certain areas should be monitored closely in the next
few months but that other areas are changing slowly and that a number of
years should elapse before reexamination of the latter areas. The following
specific recommendations are divided into two general areas—management and
research needs:
Management
1. The present balance between Na, Ca, and Mg in wastewater being applied
to the various coarse soils at Muskegon is satisfactory for crop growth and
soil structure, but the level of Na in this wastewater should not exceed
300 ppm.
2. Differential water applications should be made, with Granby soils re-
ceiving substantially less water than Rubicon or Roscommon soils, because the
Granby soil has a lower P adsorption capacity, greater potential mineraliza-
tion of native N, and possible problems with dispersion of organic matter if
Na content becomes too high.
3. Non-uniform application of wastewater should be avoided. This practice
may materially shorten the period of time that the soil is able to remove P
from the wastewater. Adsorption and degradation of organic chemicals requires
a period of time, and heavy application of wastewater may displace the or-
ganic chemicals before sufficient reaction time has occurred.
4. From a crop management viewpoint:, available Mn and Zn both appear to be
at a low level where plant deficiencies could be a problem. Sufficient Zn to
prevent deficiencies may be added in the wastewater, but decreasing organic
matter in the soils and increasing soil pH as a result of added wastewater
may decrease the availability of Mn and Zn to plants. Soil and plant Mn and
Zn levels should be monitored regularly to detect these possible deficiencies.
Research Needs
1. A detailed study should be made of N stripping in the field by agronomic
crops to determine if both the period of effective NOo uptake by crops can
be extended and if the level of N03 leaching through to groundwater can be
-------
reduced. Initial data indicates that NC>3 is leaching during periods when
the corn is not actively growing.
2. Phosphorus adsorption in the AuGres soils should be examined in detail
because it does not appear to retain P.
3. Soil physical measurements should be made again after approximately five
years of wastewater application to determine if long-term application will
affect the physical properties of very sandy soils.
4. Areas of Saugutuck and a few areas of AuGres sands that are showing an
inability to remove water through the installed drainage should be studied
to suggest a management practice or improved drainage system that would
function in these areas.
5. A close study of available heavy metals should be made in the next year.
The quantity of Zn, for example, that was supposed to have been added in the
wastewater should have been detectable in the soil but it was not found
during the first year after wastewater was applied.
6. The monitoring of pesticides in soils at special study sites and of
waters at various stages of treatment should continue to confirm develop-
mental trends observed to date. Additional flow points should be sampled to
increase the probability of detecting chemicals which enter sporadically.
7. Routine monitoring for critical trace organics in waters at key flow
points within the collection and treatment systems is essential for rational
management. This can best be done by personnel and facilities at the
Muskegon site. Timely notification of anticipated critical discharges from
connected industries will be essential.
8. An ordering of priorities among critical compounds considered for monitor-
ing is essential to allow for development of analytical capabilities and meth-
ods appropriate for different classes of compounds and realistic in relation
to available facilities, personnel and funds. Methods for a given chemical
or group of chemicals should be evaluated and quality control parameters es-
tablished before routine monitoring is undertaken. Chromatographic entities,
when first encountered, should be identified by definitive methods.
9. Supporting research is needed to identify mechanisms affecting the fate
of trace organics in pretreatment basins, storage lagoons and soil. There
should be continuing concern for the possibility that specific toxicants
might be transferred from wastewaters or sludges into animal feeds and human
food channels.
10. Computerization will be required to accumulate, retrieve and manipulate
the many kinds of information, from many sources, that are relevant to the
management and regulation of these systems. Modeling studies should continue
to this end.
-------
SECTION III
INTRODUCTION
The methods of treating waste in the past have satisfactorily reduced BOD
but have not removed nutrients. Discharge of effluents after primary and/or
secondary treatment have often led to deterioration of rivers and lakes due
to inputs of nutrients as well as organic matter. Federal and state regula-
tions now require that wastewaters be minimally polluting when they are dis-
charged into our waterways. Land treatment of wastewater is one alternative
in removing polluting materials. This method may be effective in the treat-
ment process, and it is also cost-effective in many cases; but equally im-
portant, it offers a method of treatment that recycles a portion of the
nutrients directly back into the food chain, thereby offering conservation
of nutrients.
Soil types are of prime importance in considering various land treatment
alternatives. Fine-textured soils offer considerable advantage in that they
are able to adsorb high quantities of P and other materials, but they have
a major disadvantage in that they are unable to receive high rates of water.
Oftentimes an application of just 2.5 cm of wastewater per week (1 inch), in
addition to the normal rainfall, may lead to reduced aeration and poor yields.
They would also require a considerable length of time after no water is ap-
plied before they could be farmed.
On the other end of the spectrum are the very sandy soils whose infiltration
rate and hydraulic conductivity are very high. These soils can hydraulically
receive considerable quantities of wastewater without aeration problems, but
may not adequately remove P and other nutrients because of their low adsorp-
tion capacity, particularly at high rates of wastewater application. Drainage
classification is another very important factor that must be considered in
selection of soil types for land disposal. Since wastewater must move through
the soil for treatment, it is imperative that the drainage of the soil either
be good naturally or be developed into a good drainage system by the instal-
lation of tile drainage lines.
Some soils are poorly drained because of a very slowly permeable clay layer
somewhere in the subsoil. Installation of tile lines above this layer may
easily remove the excess water if the hydraulic conductivity of the upper pro-
file is adequate.
Land treatment of wastewater is different from other more conventional methods.
The performance of a land treatment system may be much better for its first
few years of operation than thereafter because of the many sorptive and ex-
change reactions occurring in the soil which act as a buffer against rapid
-------
change. Thus a system may appear satisfactory during the first few years of
operation but then suddenly begin to leak nutrients to the drainage water.
Early detection of the changes that occur in the soil after application of
effluent, therefore, becomes of major importance in estimating the life of
the system and in showing operational changes that must be made to prolong
the life or to produce a higher quality of effluent.
At the present time the Muskegon project is the largest land treatment sys-
tem in the United States. It also has some unique features that make it
different from most other land treatment systems. The site has very sandy,
level soils, approximately two-thirds of which are, or were in their natural
state, poorly drained due to the presence of a clay layer in the subsoils.
This clay layer varies in depth but, before drainage, effectively kept a high
water table under a large acreage on the treatment site. These soils have
a very high hydraulic conductivity so that they remove water easily where a
satisfactory tile drainage system has been installed. This site was marginal
from an agricultural viewpoint without the installation of a drainage system
and the application of water and nutrients during the growing season. The
installation of drainage and irrigation systems necessary for treatment of
wastewater is converting this marginal land into productive agricultural land.
Because of the necessity of increasing xvorld food production, simultaneous
renovation of wastewater and its use to produce food is an important feature
of the Muskegon system.
The wastewater being applied to the land at Muskegon is lower than average
in nutrient content due to dilution by industrial wastewater from the S. D.
Warren Paper Company. Consequently, the M and P contents of the wastewater
after aeration and lagoon storage are about half that of an average effluent.
This has two important consequences: 1) the requirement for P removal will
not be as high, and the low P adsorption capacity of the sandy soils at Mus-
kegon is of less importance than it might be for other wastewaters, and 2)
the N content of the wastewater is sufficiently low that an agronomic crop
may be expected to be N deficient during much of the growing season; thus,
management of this system must consider the application of N during the crit-
ical periods of growth.
To construct and make the Muskegon land treatment system fully operational,
land was cleared where the native vegetation was shrubs and trees, drainage
systems installed (usually tile) where necessary, and the land surface was
tilled until it became suitable for growth of crops capable of removing nut-
rients from the wastewater.
During these clearing and construction phases, many changes may occur in the
soil properties, both chemical and physical. Drainage and cultivation are
expected to produce better aeration of the soil and result in decomposition
of soil organic matter. As a result, total soil C may decrease. With the
decomposition of organic matter also comes the release of N through ammonifi-
cation and then oxidation of NH^ to NC^. The results may be an increase in
NCL in the drainage waters.
The relative distribution of bases (Ca, Mg, and Na) in soil at various depths
to the groundwater table is not expected to change greatly with the initial
10
-------
preparation of the site, but they will change rapidly with the addition of
wastewater. Soil pH, a related chemical property, is expected to increase
with application of wastewater due to the replacement of H with basic
cations.
Heavy metals may be associated with the organic matter in the soil. Conse-
quently, oxidation of the organic matter may cause a redistribution of the
heavy metals. Also, pH and oxidation changes within the soil profile would
be expected to exert major changes on the solubility of heavy metals and the
distribution between organic and precipitated phases.
A major goal of this study was to determine soil chemical and physical proper-
ties prior to and during preparation of the site; and, once having established
this baseline data, being able to clearly delineate changes brought about by
the application of wastewater to the land as separate from changes brought
about during preparation of the site.
The objectives of the study were to:
1. Determine the quantity of N and C adsorbed or stabilized by other means
in the various soils.
2. Determine the quantity of P, K, Ca, Mg, Zn, Cu, Mn, Fe, Pb, Hg, Cr, and
Na adsorbed by soils.
3. Determine the changes in physical properties of the major soil series
receiving effluent.
4. Monitor electron-capturing organic species in soils, in incoming waste-
waters, and in drainage at outfalls.
5. Prepare soil samples for preservation as background and base level
samples for future measurements of other ions of interest.
To accomplish these objectives, a major portion of this study was devoted to
establishing the background for the site and the variability in the soils
that could be expected.
Detailed data have been reported in many quarterly reports over the past three
years. In the case of mineral analyses and physical measurements, only sum-
mary data will be included in this final report. Table 1 has been prepared
to show the location of previously reported data. All data collected to date
for pesticides and other trace organics are reported here and should super-
sede previously reported data.
A knowledge of the water applied to each of the individual circles or sites
is important in interpretation of the data; consequently, a table has been
included from data furnished by the County of Muskegon indicating the quantity
of water that was applied by sampling periods (Table 2). Total ion concen-
trations, together with sampling dates, are included in Table 3. Specific
site locations are given in Figure 1.
11
-------
Table 1. LIST OF CHEMICAL ANALYSES DATA REPORTED DURING PROJECT PERIOD.
Parameter
Extractable
NH4, P, K, Ca
Mg, and Na
Soluble N03
PH
Total
N, C, P, K, Ca,
Mg, and Na
Extractable
Fe, Mn, Zn,
Cu, Pb, and Hg
Total
Fe, Mn, Zn,
Cu, Pb, and Hg
Table
No.
1
1
1
1
1
1
1
1
2
2
2
2
3
3
3
3
Sampling
Period
1
1
2
3
4
5
6
7
1
2
3
4, 5, 6, 7
1
2
3
4, 5, 6, 7
Sites
Reported
1-8, 10-12, 14-26
28-32
9, 13, 27, 33-37
1-37
1-37
1-37
1-6, 10-12, 14-15,
18-19, 21-23
1-37
1-37
1-5, 8, 10-21, 23-31
6, 7, 9, 22, 32-37
1-37
1-37
1-37
1-37
1-37
1-37
1-37
Report
Date
April 1973
April 1975
April 1974
June 1974
April 1975
Sept. 1975
April 1976
April 1976
Oct. 1973
April 1975
April 1975
April 1975
April 1976
April 1975
April 1975
April 1975
April 1976
12
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Table 2. WASTEWATER APPLICATION TO SAMPLING SITES*.
c
Site
No
01
02
10
11
12
14
18
19
09
13
15
16
17
20
21
23
28
03
04
05
22
25
33
34
07
08
24
26
27
35
36
37
lircl
No
5
8
2
1
22
11
3
7
42
31
12
41
42
40
19
27
44
21
24
23
20
40
33
30
46
47
44
44
40
43
46
42
.e 1
Soil Type ]
Rubicon Sand
Rubicon Sand
Rubicon Sand
Rubicon Sand
Rubicon Sand
Rubicon Sand
Rubicon Sand
Rubicon Sand
Roscommon Sand
Roscommon Sand
Roscommon Sand
Roscommon Sand
Roscommon Sand
Roscommon Sand
Roscommon Sand
Roscommon Sand
Roscommon Sand
AuGres Sand
AuGres Sand
AuGres Sand
AuGres Sand
AuGres Sand
AuGres Sand
AuGres Sand
Granby Sand
Granby Sand
Granby Sand
Granby Sand
Granby Sand
Granby Sand
Granby Sand
Granby Sand
toy 74
to
Dec 74 .
216
214
212
149
196
200
196
232
55
53
193
75
55
48
139
172
36
144
181
171
173
58
64
32
71
41
36
36
48
51
71
55
Jan 75
to
Jun I,1 75
57
57
67
68
28
12
0
57
0
7
23
14
0
7
0
19
15
29
24
33
24
7
0
0
13
9
15
15
7
10
13
0
Jun 2
to
Sep 1,'7!
104
94
74
60
87
102
102
112
115
86
80
46
115
31
71
92
19
75
84
69
75
31
77
84
21
122
19
19
31
26
21
115
Sep 1
to
i Dec 33, '75
74
58
67
53
68
44
74
61
3
18
53
7
3
11
58
43
0
58
55
54
59
11
28
0.5
0.5
4
0
0
11
0
0.5
3.2
> Totals
451
423
420
330
379
358
372
462
173
164
349
142
173
97
268
326
70
306
344
327
331
97
169
116
105
176
70
70
97
87
105
173
* Data from Dr. Demirjian, County of Muskegon
13
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Table 3. ESTIMATION OF THE QUANTITY OF NUTRIENTS APPLIED TO
SOILS THROUGH IRRIGATION WITH WASTEWATER.
Element
June
1974
N 9.1
P 2.3
K 13.9
Na 232
Ca 93
Mg 25.8
Zn 0.18
Mn 0.27
Fe 1.60
Sampling
Sept.
1974
V cr /Via
Kg/na
79.0
20,5
121
2,030
820
226
1.51
2.23
14.2
Date
June
1975
2
27.6
7.0
42.7
710
290
79.0
0.53
0.80
4.98
Sept.
1975
37.4
9.8
57.0
950
380
105
0.71
1.07
6.59
Total
Applied
V o /Via
Kg/ na
153
39.6
235
3,920
1,580
436
2.93
4.37
27.4
Three background samples were collected in 1972 and 1973 prior to
application of wastewater. Sampling dates indicated are for sam-
ples collected after application of wastewater.
Quantity of each element applied in wastewater for the sampling
period terminating on the date indicated. Data on water
applied is based on circles 1, 2, 5 and 8 which received max-
imum water application. Data for nutrient content and water
application rates from Dr. Demirjian, County of Muskegon.
14
-------
Number
Circle Number,
STORAGE LAGOONS
AppleAve. (M-46)
I 1 m',\C
Figure 1. Location of sampling sites for soils (• ) and outfalls ( (g) )
15
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SECTION IV
CHEMICAL ANALYSIS OF SOIL PROFILE SAMPLES
This section gives data and interpretation of the chemical analyses
which were performed on each of the major soil types to establish
background levels of N, P, K, Ca, Mg, Na and C, and soil pH. Changes
in these properties or quantities after application of wastewater
during the first two years of operation are reported and discussed.
The discussions are arranged in the following order: introduction;
nitrogen; calcium; magnesium, sodium and sodium adsorption ratio (SAR);
phosphorus; soil pH; total carbon; potassium; and total soil analysis.
INTRODUCTION
Two types of chemical measurements may be made in soils to reflect
changes in different ions or elements that occur because of some treat-
ment—total elemental analysis and "extractable or available" fractions
of the total. Total analysis may be very useful over a long period
of time (i.e. 10 to 50 years) but over short time periods the changes
may be too small compared with total amounts already present in soil
to really determine accurately. For example, total soil K will range
from 5,000 to 25,000 ppm K, but the fraction that is changing rapidly
may be only 25 to 100 ppm K. On the other hand, a total measurement
of heavy metal content may be adequate to detect even short-term changes.
For this study, methods have been adapted from prior soil science studies
to measure extractable and/or nutrients that are available to plants
and hence more active and more likely to move with soil water. In
most cases, these methods are expected to reflect early changes in
the status of nutrients within the soil profile. These changes, in
turn, will indicate how the system is functioning, both for agronomic
production and, more importantly, in nutrient removal. Individual
procedures are attached as appendix I to this report.
The land treatment site contains four major soil types—Rubicon sand,
Roscommon sand, AuGres sand, and Granby sand (Figure 2). These four
soil types account for more than 90 percent of the area. The Rubicon
sand is a very sandy well-drained soil with a thin organic layer on
the surface. The clearing operation (i.e., most of this was in forest
prior to development of the land treatment site) disrupted this or-
ganic layer and produced a somewhat heterogeneous surface. Both the
Roscommon and AuGres sands had high water tables prior to draining.
They are very sandy but have well aerated conditions in the surface
soils. The Granby soils have much higher organic matter contents and
have developed under high water tables. A moderate portion of these
soils have been farmed in the past.
To establish baseline data for the land treatment site, eight sites
were selected from within each of the major soil types by use of a
soil survey map of che area and by on-site inspection. After analysis
16
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Circle Number
STORAGE LAGOON'S
Apole Ave. ( M 46)
^ Rubicon Sand
/"""N AuGres Sand
Roscommon Sand
Granby Loamy Sand
Other Soil Types
Figure 2. Major soil types at Muskegon Wastewater Treatment site.
17
-------
of data from the sites, one site mapped as AuGres appeared more like
Roscommon; consequently, the final selections had eight Rubicon sands,
nine Roscommon sands, seven AuGres sands, and eight Granby sands.
The distribution of these by site and circle number are shown in Table 4.
Each sampling site consisted of a permanently marked area no greater
than 15 meters in diameter. A single profile sample was collected
twice yearly from each sampling site with a bucket auger until the
water table was reached. After the water table was encountered, a
2.5 cm plastic tube was inserted to a 305 cm depth by application of
slight vacuum. The tube with sample was withdrawn while under vacuum,
carefully placed in a sampling trough, and then separated into the
15 cm (6 inch) increments.
Samples were run in a field moist state for NO^. The moisture content
was determined concurrently so that the values could be corrected back
to oven dry moisture. All other determinations were run on air-dried
samples.
NITROGEN
Three fractions of nitrogen were measured in the soil profile samples—
soluble NO^, NH^+, and total Kjeldahl N (which included NH^+ but not
NOT). Background data was obtained by computing the mean and standard
deviation for each of the four major soil types over three sampling
periods. The individual sites were combined for each soil type as
shown in Table 4 for summer 1972, spring 1973, and fall 1973 sampling
periods, all prior to application of any wastewater. It should be
noted, however, that clearing operations and the installation of drain-
age systems during this period of sample collection did have some effect
on the N fractions.
Effect of Soil Type on the Initial Nitrogen Content of Soil Profiles
Considering first the soluble and exchangeable forms of N (NOo and
NH^+) (Tables 5 to 8), the Rubicon sand and the AuGres sand were similar
in N content. The Roscommon sand had nearly double the content of
both forms of N, and Granby sand contained about 6 times more NH/
and 10 times more NOo than either Rubicon or AuGres sand. This is
somewhat reflected in the values for total N (Tables 9 to 12) in that
Rubicon was much lower than AuGres and Roscommon, all of which were
many times lower than Granby. The N contents reflect the soil develop-
ment. Rubicon sand is a well-drained sand developed under forest with
a deep water table—generally deeper than 7 meters. This led to de-
velopment of a soil profile that was low in total N because the aer-
ation caused decomposition of much of the organic matter. The organic
matter present was in a relatively thin layer on the surface of the
soil. Both AuGres and Roscommon were developed under a fluctuating
water table. While the AuGres soil was well aerated during the summer
months, the water table may have come to within 60 cm of the surface
during early spring. Roscommon sand is similar, but the water table
18
-------
Table 4. SITES COMBINED IN SUMMARIZING EACH SOIL TYPE
Rubicon Roscommon Augres Granby
Sand Sand Sand Sand
sites
01 09 03 07
02 13 04 08
10 15 05 24
11 16 22 26
12 17 25 27
14 20 33 35
18 21 34 36
19 23 37
28
19
-------
Table 5. MEAN AND STANDARD DEVIATIONS FOR EXTRACTABLE AND SOLUBLE NUTRIENT CONTENT OF SOILS
FROM MUSKEGON SPRAY AREA-BASELINE DATA RUBICON SAND.
NJ
O
NO 3
K
Ca
* Mean of 8 sites (see Table 2) and 3 sampling dates (7/72, 6/73 and 9/73).
** Standard deviation.
PH
Depth
cm
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
244-259
259-274
274-290
290-305
X*
5.4
3.8
2.9
2.5
2.3
2.1
2.2
2.0
1.8
2.0
1.9
2.0
2.0
2.5
2.0
1.6
1.5
2.0
2.1
1.9
SD**
5.9
3.6
2.1
2.3
2.0
2.2
1.9
2.2
1.8
2.2
2.0
2.1
2.0
2.7
2.1
1.7
1.6
2.3
2.6
2.7
X
2.8
1.6
1.4
1.3
1.2
1.2
1.1
1.0
1.1
1.0
0.9
0.9
1.0
0.9
0.9
0.9
0.9
0.8
0.8
0.8
SD
4.4
1.9
1.3
1.3
1.4
1.2
0.9
0.8
0.8
0.7
0.5
0.5
0.5
0.3
0.4
0.6
0.4
0.3
0.3
0.3
X
26
24
25
31
32
27
21
20
18
16
16
15
13
12
13
12
12
12
10
11
SD
13
15
13
14
15
14
10
9
9
8
9
6
5
5
5
5
5
6
5
5
X
21
13
11
9
6
5
4
4
4
4
4
4
13
6
4
5
5
5
13
5
SD
14
9
5
6
4
3
2
1
1
2
1
2
43
8
1
2
2
2
40
2
X
-ppra —
82
47
35
25
17
15
14
15
16
14
17
19
26
24
31
25
26
35
52
73
SD
59
40
31
21
16
15
13
12
15
12
15
17
35
31
38
20
21
37
79
203
X
8
5
4
3
1
1
1
2
3
2
2
3
3
3
3
4
5
6
6
6
SD
5
3
3
2
1
1
0.9
3
7
3
3
3
4
4
4
5
6
8
7
7
X
10.9
8.7
8.2
8.5
8.5
9.5
7.3
6.9
7.0
7.7
7.5
8.6
9.4
8.6
8.0
8.6
9.0
8.3
9.4
8.8
SD
12.9
8.7
10.2
12.4
13.0
14.1
9.1
9.6
9.0
9.6
10.7
12.8
12.8
12.8
10.1
11.9
13.2
12.6
13.0
12.8
X
5.0
5.1
5.3
5.3
5.3
5.3
5.4
5.5
5.6
5.6
5.6
5.7
5.7
5.8
5.9
5.9
5.9
6.0
6.0
6.1
SD
0.4
0.4
0.4
0.4
0.4
0.4
0.4
0.4
0.6
0.5
0.5
0.5
0.7
0.7
0.6
0.7
0.6
0.7
0.8
0.8
-------
Table 6. MEAN AND STANDARD DEVIATIONS FOR EXTRACTABLE AND SOLUBLE NUTRIENT CONTENT OF SOILS
FROM MUSKEGON SPRAY AREA-BASELINE DATA ROSCOMMON SAND.
Depth
cm
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
244-259
259-274
274-290
290-305
Nl
X*
10.0
8.7
3.8
2.8
2.4
2.b
2.3
2.8
2.1
2.3
2.4
2.6
2.1
2.1
2.5
2.1
2.6
2.5
2.4
2.7
Ii»
SD**
23.3
17.9
4.4
2.3
2.1
2.4
2.0
3.2
2.2
2.2
1.9
2.4
2.0
1.9
2.4
2.0
2.2
2.3
2.5
2.9
t
X
6.0
6.9
3.1
2.3
1.5
1.3
1.4
1.4
1.0
1.2
1.0
1.0
1.0
0.9
1.0
0.9
0.9
0.9
0.9
0.9
10 3
SD
12.4
12.3
4.3
3.0
1.0
1.4
1.7
1.7
0.5
0.6
0.4
0.6
0.4
0.4
0.4
0.4
0.3
0.3
0.3
0.3
I
X
9.6
7.9
5.6
7.2
9.1
8.4
8.6
9.0
9.2
9.6
9.2
8.9
8.2
8.9
8.3
8.0
7.5
7.3
7.7
8.0
>
SD
5.8
5.6
3.9
7.0
7.7
6.8
7.3
8.2
7.9
9.0
7.8
7.1
6.0
7.4
6.7
5.7
5.4
5.9
6.3
6.2
F
X
33
17
9
7
7
7
7
7
7
7
7
7
6
7
6
7
6
6
6
6
r
SD
23
10
7
4
3
4
4
4
4
4
6
7
5
5
3
5
4
3
4
3
C
X
420
240
130
200
110
96
130
110
140
220
210
120
96
100
94
95
93
93
120
130
;a
SD
430
240
140
580
210
83
230
110
230
460
420
230
130
140
140
140
120
120
180
180
W
X
78
44
11
10
13
17
23
26
27
26
22
20
21
23
24
23
25
22
23
24
lg
SD
150
110
13
15
29
34
48
49
50
52
48
44
49
52
50
44
45
40
39
41
K
X
11.0
9.2
8.0
7.5
7.5
9.4
9.6
8.6
9.9
10.5
11.1
9.0
8.6
9.3
9.4
9.6
9.5
10.1
11.0
10.3
[a
SD
8.9
8.4
9.1
8.7
9.2
13.1
12.5
12.0
13.4
17.8
17.2
12.2
10.9
12.1
11.4
13.4
12.8
12.3
11.8
11.9
P
X
5.6
5.6
5.8
6.0
6.0
6.2
6.2
6.3
6.2
6.2
6.2
5.9
5.7
5.7
5.7
5.7
5.7
5.8
6.0
6.1
>H
SD
0.7
0.9
0.9
0.9
0.9
0.9
1.0
1.0
1.0
1.1
1.2
1.0
1.1
1.1
1.1
1.2
1.2
1.1
1.2
1.2
* Mean of 9 sites (see Table 2) and 3 sampling dates (7/72, 6/73 and 9/73).
** Standard deviation.
-------
Table 7. MEAN AND STANDARD DEVIATIONS FOR EXTRACTABLE AND SOLUBLE NUTRIENT CONTENT OF SOILS
FROM MUSKEGON SPRAY AREA-BASELINE DATA AUGRES SAND.
10
Depth
t*>Tn
CIu
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
244-259
259-274
274-290
290-305
NI
X*
4.8
2.5
2.1
2.0
2.4
1.7
1.5
1.6
2.0
1.7
1.9
2.0
1.7
1.8
2.0
1.7
1.9
2.0
1.9
1.9
i«f
SD**
8.7
3.0
2.1
2.0
4.1
2.0
1.5
1.8
2.5
2.2
1.8
2.3
2.3
2.4
2.9
2.6
2.7
3.1
2.8
3.4
1
X
3.6
2.2
1.9
1.7
1.4
1.5
1.2
1.1
1.0
1.0
1.0
1.0
1.1
1.2
1.0
1.0
1.0
1.0
1.1
1.1
SO 3
SD
5.8
2.4
2.9
2.6
1.4
2.0
1.0
0.9
0.7
0.7
0.7
0.8
0.9
1.0
0.7
0.7
0.8
0.9
1.2
1.2
I
X
11.5
7.1
5.5
7.1
9.1
11.0
10.7
11.2
10.8
11.0
12.9
10.6
10.1
10.4
10.1
10.0
10.0
9.5
9.1
8.6
3
SD
12.2
10.7
5.6
6.8
6.4
9.0
8.4
7.5
7.0
6.5
6.1
5.4
5.8
6.5
6.6
8.3
8.8
7.7
7.0
7.0
I
X
32
21
9
6
5
6
5
5
5
8
5
5
5
5
5
5
6
8
6
7
C
SD
— ppt
20
30
6
5
2
4
2
2
2
11
2
3
2
2
3
2
4
11
2
5
C
X
310
210
100
67
51
61
47
54
50
43
32
45
43
40
86
130
120
140
100
170
:a
SD
260
200
82
56
55
66
44
50
64
57
25
52
55
47
161
280
280
290
190
290
1
X
49
37
20
8
6
8
6
9
7
8
7
8
10
10
8
8
8
11
16
16
-------
Table 8. MEAN AND STANDARD DEVIATIONS FOR EXTRACTABLE AND SOLUBLE NUTRIENT CONTENT OF SOILS
FROM MUSKEGON SPRAY AREA-BASELINE DATA GRANBY SAND.
NJ
Depth
n m
cm
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
244-259
259-274
274-290
290-305
NI
X*
39.2
10.6
3.9
2.5
2.5
1.6
1.9
1.3
1.6
1.6
1.2
1.1
1.0
1.0
1.1
1.0
1.5
1.3
1.3
1.4
I«*
SD**
80.7
19.8
6.3
2.5
4.8
1.6
2.0
1.3
2.3
2.0
1.2
1.4
1.1
1.1
1.3
1.1
2.5
2.0
2.1
2.6
NC
X
34.3
18.6
8.1
3.1
2.4
1.7
1.5
1.2
1.3
1.3
1.3
1.2
1.3
1.3
1.2
1.2
1.1
1.2
1.1
1.1
'3
SD
80.2
41.4
17.1
3.3
2.2
1.1
0.9
0.6
0.6
0.7
0.8
0.6
0.9
0.9
0.7
0.5
0.4
0.5
0.5
0.6
E
X
17.8
7.8
4.9
5.1
5.1
5.9
6.5
8.0
7.0
6.8
6.9
7.2
7.4
6.8
6.3
6.6
6.7
6.0
6.4
6.3
i
SD
16.9
6.9
4.2
5.2
4.2
4.3
4.4
5.4
4.4
4.3
3.6
3.8
3.8
3.7
3.9
4.2
4.9
4.5
4.5
4.5
X
84
37
17
13
10
10
9
7
8
7
7
6
6
5
5
6
5
6
6
6
K
SD
PF
69
31
12
11
4
7
4
3
4
3
3
3
3
2
2
4
3
3
4
2
Ca
X
1970
1920
1230
770
565
440
390
340
330
360
335
320
310
300
340
295
320
335
310
340
i
SD
1830
2650
1680
1100
880
680
680
660
700
700
640
655
616
600
590
560
580
540
530
590
V.
X
210
190
140
110
110
110
110
100
100
110
100
93
86
91
94
92
90
100
91
100
lg
SD
450
430
330
340
340
410
400
390
390
390
360
340
310
350
320
320
320
340
310
320
Na
X
21.3
21.4
15.7
12.5
10.9
9.2
7.6
7.1
7.1
7.1
7.8
7.2
7.7
6.8
7.6
6.4
7.4
7.2
7.4
6.9
L
SD
12.4
17.7
14.4
10.9
8.8
8.3
5.8
6.0
5.0
5.1
9.3
5.7
7.0
5.0
8.4
4.0
7.1
5.0
5.5
4.8
1
X
6.4
6.3
6.4
6.6
6.6
6.4
5.8
5.1
5.2
4.9
4.9
4.7
4.7
4.7
6.0
5.2
5.4
5.6
5.5
5.6
PH
SD
0.8
0.7
0.9
0.8
0.8
1.2
1.6
1.7
1.8
1.8-
1.3
1.8
1.9
1.9
2.1
2.0
1.8
1.8
1.8
1.8
* Mean of 8 sites (see Table 2) and 3 sampling dates (7/72, 6/73 and 9/73)
** Standard deviation.
-------
Table 9. MEAN AND STANDARD DEVIATION FOR TOTAL NUTRIENTS OF SOILS FROM
MUSKEGON SPRAY AREA-BASELINE DATA RUBICON SAND.
K
Me
Na
NJ
-P-
Depth
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
244-259
259-274
274-290
290-305
X*
490
280
180
130
92
71
56
51
42
35
44
34
33
32
30
34
32
31
29
31
SD**
160
67
57
41
31
43
24
25
20
18
18
13
19
19
16
27
21
14
12
18
X
.93
.49
.39
.21
.15
.21
.15
.14
.16
.15
.14
.14
.12
.09
.16
.11
.11
.12
.11
.11
SD
.31
.26
.21
.13
.14
.19
.20
.14
.18
.16
.17
.15
.11
.10
.21
.13
.09
,11
.13
.12
X
280
240
220
200
160
140
130
130
110
110
160
110
91
97
98
110
100
100
99
93
SD
140
110
130
90
62
52
47
60
40
43
180
73
37
42
44
66
49
48
39
46
X
9700
9400
10200
10000
9200
9500
9700
9100
9300
13100
9800
8800
8500
18800
8600
8700
8700
9100
9000
8900
SD
3400
3300
3200
2900
2600
3000
2800
2500
2500
18100
1700
3100
2900
50600
2300
2100
2300
2700
2900
2500
X
1800
1800
1800
1700
2000
2100
1800
2100
2000
1900
2100
2200
1900
1900
2200
2200
2400
2600
3100
3300
SD
1000
1000
900
800
1100
1500
800
1400
1600
1300
1100
1400
1000
1100
1400
1300
1200
1700
1800
3300
X
870
870
990
850
900
860
1110
1030
860
810
960
910
810
750
870
970
860
1000
1000
1270
SD
420
410
630
330
340
520
1640
640
640
390
390
400
380
310
410
720
380
700
520
1530
X
3560
3730
3840
4220
4120
4130
4290
4830
4200
4780
5530
4710
4620
4850
4540
5270
5530
4710
4960
4460
SD
1690
1810
1920
1890
2020
1820
2550
2950
2020
2580
4780
2070
3060
3680
2200
3530
3130
2100
3420
1680
* Mean of 8 sites (see Table 2) and 3 sampling dates (7/72, 6/73 and 9/73).
** Standard deviation.
-------
Table 10. MEAN AND STANDARD DEVIATION FOR TOTAL NUTRIENTS OF SOILS FROM MUSKEGON
SPRAY AREA-BASELINE DATA ROSCOMMON SAND.
N3
Ui
Depth
r*m
(~IH
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
244-259
259-274
274-290
290-305
t
X*
990
610
220
100
89
61
48
50
39
36
34
31
28
26
30
32
27
26
26
26
I
SD**
440
370
170
52
86
25
24
29
13
12
14
9
9
11
21
24
14
11
12
11
C
X
1.48
.97
.61
.37
.31
.29
.28
.30
.26
.24
.24
.20
.21
.20
.20
.18
.18
.19
.20
.22
SD
.46
.66
.69
.28
.19
.18
.17
.21
.21
.18
.20
.17
.16
.17
.16
.19
.14
.17
.18
.18
E
X
190
160
150
95
92
100
110
110
100
100
110
100
110
97
100
94
100
100
91
90
>
SD
120
110
150
35
26
43
57
70
53
50
79
48
46
42
51
40
57
59
41
41
K
X
8800
10100
10200
10700
10600
10800
10900
11000
12000
10300
9700
11100
10100
9800
11100
9900
9700
13100
9900
9700
SD
- ppm
2400
2400
2500
2900
2700
3100
3100
2800
4500
3000
3700
2600
2500
2000
2700
2700
3000
17300
3000
2400
Ca
X
2700
2500
2400
2700
2600
3300
3100
3600
3300
4100
3300
3000
2700
3100
3600
3400
3500
3900
3900
4200
SD
1700
2000
1300
1700
2400
3300
2800
3200
2300
3300
2300
1800
1700
2000
2700
2500
2400
3200
3800
4300
Mg
X
780
600
660
880
830
950
970
1130
1350
1490
1160
950
980
970
1110
1140
1280
1540
1400
1500
r
SD
590
386
326
830
750
1000
1080
1080
1780
1780
1100
820
920
790
990
1130
1140
1980
1400
1990
Na
X
3420
3690
4160
4050
4410
4890
3650
4560
4480
3880
4010
4320
3730
3880
4140
3940
3700
3860
3680
3680
SD
1720
1600
1790
1410
1620
3140
2550
2440
1830
1250
2550
1540
1270
1270
1330
1700
1470
1650
1130
1110
* Mean of 9 sites (see Table 2) and 3 sampling dates (7/72, 6/73 and 9/73).
** Standard deviation.
-------
Table 11. MEAN AND STANDARD DEVIATION OF TOTAL NUTRIENTS OF SOILS FROM
MUSKEGON SPRAY AREA-BASELINE DATA AUGRES SAND.
Depth
cm
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
244-259
259-274
274-290
290-305
1
X*
850
540
280
150
120
75
66
57
52
43
42
34
33
29
30
28
27
27
28
27
-------
Table 12. MEAN AND STANDARD DEVIATION OF TOTAL NUTRIENTS OF SOILS FROM
MUSKEGON SPRAY AREA-BASELINE DATA GRANBY SAND.
ISJ
-vj
Depth
Cm
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
244-259
259-274
274-290
290-305
X*
2800
2120
1260
670
330
140
100
90
64
49
51
47
36
32
33
37
36
39
32
30
N
SD**
1900
1930
1610
900
440
130
88
84
37
23
23
23
17
13
17
23
18
25
13
16
C
X
3.21
3.24
2.14
1.51
1.05
.37
.32
.32
.28
.28
.27
.26
.24
.22
.25
.25
.28
.28
.26
.26
SD
2.42
4.59
3.95
3.06
2.69
.31
.31
.30
.29
.25
.27
.24
.24
.25
.26
.26
.35
.36
.33
.32
I
X
310
320
160
130
120
110
130
130
120
110
120
100
100
100
110
100
150
130
98
110
>
SD
260
470
140
63
60
58
98
68
54
54
80
52
46
58
53
52
270
150
57
81
I
X
10100
11100
11500
11500
12100
11800
12600
12300
12100
11400
11500
11600
11900
11300
11700
11100
11700
11600
11100
11300
r
SD
3000
2900
3000
2800
2000
2200
3100
3700
3400
3400
3500
3200
2900
3400
3800
3900
3300
3200
3000
3500
C,
X
9200
13400
15900
11300
7700
3800
4300
4500
4500
5000
4900
4800
4500
5000
4500
4500
4400
4700
4400
5500
a
SD
11400
24700
32800
25700
15400
3000
3900
4000
4300
5000
4600
4300
4000
4500
3900
3800
3400
3900
4100
5300
Mg
X
1300
1300
1300
1600
1500
1100
1200
1400
1400
1400
1500
1500
1300
1200
1300
1400
1400
1500
1400
1600
r
SD
1000
900
1100
2000
1700
700
1200
1300
1300
1200
1500
1600
1100
1100
1100
1100
1100
1300
1400
1400
Na
X
4270
4510
5320
5540
4480
4720
4970
4940
4490
4120
4120
4310
4380
4250
4480
4050
4190
3940
4250
4240
i
SD
1600
1180
2740
4030
1510
1260
2300
1210
1040
790
890
1250
1060
1190
1420
1210
1130
1090
1310
1490
* Mean of 8 sites (see Table 2) and 3 sampling dates (7/72, 6/73 and 9/73).
** Standard deviation.
-------
will be somewhat closer to the surface during the winter and spring
months. The Granby soil has had a high water table—at the surface
during many months of the year—unless artificial drainage has been
installed. This has led to accumulation of organic matter in the
Granby soil with the result of high total N and, in many cases, also
high soluble forms of N.
Effect of Drainage and Farming on Nitrogen Distribution in Soil Profiles
Installation of tile drainage systems and farming these sandy soils
resulted in at least two independent effects. First, draining these
areas removed free water and allowed the soil profiles to be leached
of soluble nutrients. Most notable was NOT which moves with the water.
Individual site 15 (circle 12) is an example of this effect. At the
first sampling the nitrate content of the 0-15 cm (0-6 inch) layer
was 9.4 ppm N as NC^, and the 15-30 cm (6-12 inch) layer was 19.5 ppm
N. All other layers in this profile were less than 1 ppm N except
for the 107-122 cm (42-48 inch) and the 229-244 cm (90-96 inch) layer
(2.26 and 2.51 ppm N as NO,,, respectively). By the second sampling
taken during the spring of the following year, the levels of NOT were
less than 1 ppm N at all depths in the soil profile, indicating that
the NOT had been removed from the profile by leaching.
The second effect is the increased production of NH, and NOT by miner-
alization of organic matter due to increased aeration after drainage.
The best example of this occurred at site 35 (circle 43) on a Granby
sand (Table 13) . The NH^4" content was high in the 0-15 cm layer at
the time of the first sampling (120 ppm N) with levels decreasing in
the 15-30 cm (18.5 ppm N) and 15-46 cm (13.1 ppm N) layers. At greater
depths the quantities of NH/ were quite low. Nitrate N was low through-
out the profile with a high value of 3.51 ppm N as NO^ in the 0-15
cm layer. By the second sampling the following spring, the soil content
of both NH, and N0o+ were very high in the surface layers (see Table
13). It appears that with the time between the first and second samp-
ling, ammonification had progressed to a great degree and some nitri-
fication had occurred. The band of higher NH,+ and NOo at 61-76 cm
suggests that the movement downward of the N had not occurred at a
fast rate.
By the fall of 1973 the NH values were lower than in the spring but
still quite high. The samples collected in the spring of 1974 were
very low in NH,+ and not really very high, comparatively speaking,
in NO^. Three possibilities exist for the removal of the large quan-
tities of NH, and NOT. First, plant uptake could account for a por-
tion of the removal but not between fall 1973 and spring 1974. Second,
leaching of N0~ may have occurred. This should have lead to higher
values of NO^ in the lower horizons of the soil profile. This, in
fact, occurred in the spring 1974 sampling where values as high as
5.52 ppm N as NO^ occurred in the soil at 290-305 cm depth. It should
be pointed out that this 5.52 ppm concentration is on a dry weight
basis in the soil and the solution concentration would be considerably
28
-------
Table 13. AMMONIUM AND NITRATE CONTENTS OF THE SOIL PROFILE AT SITE 35
(GRANBY SAND).
Depth
cm
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
244-259
259-274
274-290
290-305
Summer
NH.
4
120.0
18.5
13.1
3.4
2.5
1.3
5.4
1.5
1.4
. 1.0
2.2
2.6
1.0
1.1
1.1
1.2
0.9
0.8
0.9
0.9
1972
N03
3.5
2.1
1.5
1.6
1.5
1.4
1.3
1.2
1.8
1.8
2.0
1.3
1.6
1.6
1.8
1.8
1.8
1.8
2.0
1.8
Spring
NH4
324
71
29
7.7
24
3.0
6.2
2.6
4.7
2.4
2.6
1.8
2.5
1.8
1.5
0.9
0.9
1.8
2 1
2.1
1973
N03
VI
96
|22
13
2.6
8.3
1.7
1.9
1.5
1.8
1.4
1.2
1.4
1.7
1.6
1.5
1.3
0.7
1.1
1.1
1.2
Fall
NH.
4
177
31
12
8
2.0
2.3
3.0
2.3
2.7
2.0
1.5
1.8
1.0
.5
.8
.8
.5
.8
1.5
1.5
1973
N03
59
13
3.0
1.6
1.0
0.9
0.8
0.6
0.6
0.6
0.6
0.6
0.6
0.6
0.5
0.5
0.5
0.7
0.5
0.5
Spring
NH.
4
0.6
*
1.2
*
1.8
0.6
1.2
*
0.6
1.8
1.2
*
2.4
1.2
1.8
*
0.3
1.8
0.6
1.2
1974
N03
14
12
4.9
4.1
2.9
3.4
1.8
2.1
1.6
1.8
1.7
2.0
2.1
2.6
1.8
1.3
1.3
1.6
4.6
5.5
29
-------
higher (probably greater than 20 ppm N as NOo in the ground water at
this depth). The third possibility is that considerable denitrification
may have occurred within this profile. This is suggested by the low
values of NOo throughout the lower layers of the profile. This is
a reasonable reaction to expect in that the NHL was being nitrified
in the surface layers, the Granby sand does contain considerable or-
ganic matter which may move to the lower layers and serve as an energy
source, and this soil has a high water table. But the potential does
exist for movement of high quantities of NOo into the ground water
through this profile even without the addition of wastewater. If C
diminishes in the saturated zone, the NO, may no longer be denitrified
and could lead to increased concentrations of NOo in the groundwater.
Effect of Application of Wastewater on Nitrogen Distribution in Soil
Profiles
During the initial year of operation of the system (1974) the N content
of the wastewater being applied to the fields was about 2.5 ppm N as
NH, and 2.5 ppm N as NO^ for water from the east storage lagoon and
about 1 ppm N as NH, plus NOo for water from the west lagoon (Demirjian,
1975). Soil profiles were collected, inasmuch as possible, after 20
cm (8 inches) of this wastewater had been applied. Mean values for
these nutrients are included as tables 14 to 17. With one exception,
the NH, and NO" contents of the Rubicon soil profiles were reduced
by the application of this water. Site number 01, however, was very
high in NH, which is affecting the averages presented in table 14.
Table 18 has been included to compare site 01 with the average of the
other 7 sites. It is felt that site 01 must have been in an area where
rapid ammonification was occurring due to incorporation of organic
matter when preparing the site for farming operation. The application
of water then moved much of this NH, into the soil profile. Although
this would not be expected to happen in a soil with a large cation
exchange capacity, the Rubicon sand has a very low cation exchange
capacity which will allow for movement of cations in the profile.
The evidence of high NH^ was still present in the surface soil in
September of 1974 after the application of many inches of wastewater
but had virtually disappeared by the spring of 1975. The NH, and
NOo contents of the Roscommon and AuGres sands were low and more uni-
form with depth, but the Granby sand gave indications of some increased
NH, and NO1^ in the lower horizons after application of 20 cm (8 inches)
of wastewater.
Means have not been calculated for the later samplings since the quan-
tity of water that was applied to individual circles varied considerably.
Thus, an examination has been made of individual sites and general
conclusions drawn from this data.
After the application of rather large quantities of wastewater, the
three soil types (Rubicon, AuGres, and Roscommon) appeared to stabilize
and give rather uniformly low values for NH, and NOo. Bands of NO^
were apparent in these soils at both samplings (spring and fall 1975),
30
-------
Table 14. MEAN AND STANDARD DEVIATIONS FOR EXTRACTABLE AND SOLUBLE NUTRIENT CONTENT OF
SOILS FROM MUSKEGON SPRAY AREA AFTER EIGHT INCHES OF EFFLUENT RUBICON SAND.
Depth
r*Tn
Llll
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
244-259
259-274
274-290
290-305
NI
X*
6.3
4.4
1.2
5.6
.5
4.5
6.2
5.3
.4
.3
3.8
1.5
1.3
.4
1.8
.4
.6
4.8
5.3
1.7
^
SD**
13
10
1.7
14.1
.7
11.7
16.7
14.1
.3
.1
9.8
3.4
2.6
.4
4.1
.5
.5
12.6
14.0
3.3
NO'
X
3.5
1.6
1.2
1.0
.9
.8
.9
.8
.7
.7
.8
.7
.7
.7
.7
.6
.6
.7
1.1
1.4
3
SD
2.2
1.
.6
.4
.4
.4
.4
.4
.4
.4
.5
.4
.4
.4
.3
.2
.2
.2
.5
1.
P
X
28
22
17
25
39
29
22
19
18
17
16
14
14
11
11
11
10
11
12.05
15.7
SD
12
13
5
16
13
14
6
5
3
3
3
3
4
4
4
3
4
4
4
4
X
32
21
13
7
5
4
3
3
3
4
4
4
4
4
4
4
4
4
5
6
K
SD
pprn — •
24
28
9
3
2
1
1
1
1
2
1
1
2
1
3
1
1
1
1
2
C;
X
140
84
40
34
25
30
15
23
15
15
19
14
20
21
28
25
44
61
71
68
a
SD
70
80
21
35
35
44
16
42
13
12
15
12
18
15
26
18
42
52
102
88
MF
X
18
15
7
5
2
3
2
2
1
2
3
2
3
4
3
3
6
6
8
11
r
SD
8
18
8
5
3
4
1
3
1
2
2
2
4
5
4
3
8
7
9
15
Ns
X
19.9
10.6
8.2
7.2
4.8
4.0
3.4
3.7,
3.6
3.2
3.8
3.1
3.2
5.0
3.9
2.5
4.6
4.1
4.8
5.5
i
SD
11.3
6.4
5.1
4.9
3.4
2.4
2.1
1.8
2.3
1.7
2.3
1.8
1.5
6.5
2.6
1.4
3.3
3.6
3.0
3.9
pH
X
5.1
5.0
4.0
5.0
5.9
5.2
5.3
5.3
5.4
5.4
5.5
5.5
5.6
5.6
5.6
5.6
5.8
6.0
6.1
6.2
SD
.4
.4
.5
.5
.5
.5
.6
.6
.5
.5
.6
.5
.6
.6
.6
.5
.8
.9
.9
.7
* Mean of 8 sites (see Table 2)
** Standard deviation.
-------
Table 15. MEAN AND STANDARD DEVIATIONS FOR EXTRACTABLE AND SOLUBLE NUTRIENT CONTENT OF SOILS
FROM MUSKEGON SPRAY AREA AFTER EIGHT INCHES OF EFFLUENT ROSCOMMON SAND.
CO
Depth
cm
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
244-259
259-274
274-290
290-305
NI
X*
2.9
2.9
1.0
.9
1.2
1.3
.8
.7
.6
.5
.6
.6
.6
.7
.4
1.9
.5
.5
.5
.3
^
SD**
4.5
4.3
1.1
1.0
1.9
1.6
.8
.6
.5
.5
.4
.6
.8
.8
.4
3.8
.6
.5
.3
.3
N(
X
2.4
1.5
1.0
1.0
.9
1.3
.8
.8
.8
.8
.8
.6
.8
1.2
1.5
1.2
1.0
1.0
1.2
1.3
5 3
SD
1.5
.8
.3
.5
.5
1.6
.4
.4
.4
.4
.4
.2
.4
.8
1.3
.8
.9
.8
.9
1.0
I
X
15
10
9
10
13
15
10
11
11
11
10
10
10
8
7
8
8
8
7
7
•>
SD
15
8
6
10
13
15
9
5
5
5
5
6
6
5
6
6
6
5
5
5
I
X
25
19
9
8
8
6
5
6
6
6
7
6
6
6
7
7
8
8
8
8
C
SD
16
18
7
6
5
4
4
4
7
5
5
5
5
5
6
7
7
5
5
6
d
X
ppm
298
340
212
112
96
87
86
83
118
94
112
83
88
89
100
109
104
165
203
196
i
SD
197
279
88
129
81
60
121
114
222
142
146
129
119
112
139
150
138
251
330
371
M
X
45
43
28
20
14
12
12
13
19
14
22
18
20
21
24
26
26
22
23
26
R
SD
37
28
35
33
21
12
20
24
46
27
28
30
34
36
39
43
46
39
41
43
Ni
X
29.6
22.2
7.3
7.9
7.9
8.6
7.0
7.2
7.7
6.6
7.6
6.4
6.6
6.5
6.9
6.6
6.1
8.8
11.6
12.2
i
SD
20.0
20.4
3.0
6.6
7,0
8.0
7.1
7.2
11.4
8.8
8.9
7.3
7.9
5.4
8.0
6.6
5.8
9.3
14.2
12.7
P
X
6.3
6.2
6.3
6.3
6.4
6.3
6.2
6.1
5.9
6.2
6.3
6.3
6.2
6.1
6.0
6.1
6.1
6.3
6.6
6.8
H
SD
1.1
1.1
1.1
1.1
1.4
1.1
1.1
1.2
1.3
1.2
1.2
1.5
1.5
1.7
1.7
1.7
1.6
1.4
1.3
1.2
* Mean of 9 sites (see Table 2)
** Standard deviation.
-------
Table 16. MEAN AND STANDARD DEVIATION FOR EXTRACTABLE AND SOLUBLE NUTRIENT CONTENT OF SOILS
FROM MUSKEGON SPRAY AREA AFTER EIGHT INCHES OF EFFLUENT AUGRES SAND.
NH,
NO.
K
Ca
Mg
Na
PH
Lo
Depth
r*Tn
Cul
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
244-259
259-274
274-290
290-305
X*
3.8
2.6
1.3
.8
.6
.6
.3
.3
.5
.4
.5
.7
.2
.5
.4
.7
.3
.3
.3
.3
SD**
5.5
5.1
.7
.6
.5
.3
.4
.3
.5
.5
.3
.8
.2
.4
.4
.8
.3
.2
.3
.1
X
6.2
4.7
2.9
2.3
2.1
2.0
1.6
1.6
1.5
1.4
1.6
1.5
1.7
1.5
1.4
2.0
1.9
2.2
2.2
2.3
SD
4.4
3.7
2.2
1.3
2.0
1.9
1.3
1.4
1.2
1.2
1.4
1.2
1.5
1.1
1.2
1.5
1.4
1.6
1.4
1.5
X
17
9
10
10
12
10
10
12
12
15
13
13
18
14
14
13
13
12
12
11
SD
17
9
7
9
9
5
5
7
9
11
8
10
14
9
10
11
11
8
8
8
X
33
16
10
6
4
4
3
4
3
4
4
4
4
4
4
4
5
4
5
6
SD
15
8
7
4
3
2
1
1
2
2
2
2
2
3
2
2
3
3
3
2
X
410
230
160
140
66
53
41
31
33
44
38
33
25
25
29
30
35
47
240
280
SD
230
170
200
210
69
49
33
1 32
25
36
27
19
19
31
26
26
28
28
490
590
X
40
22
12
9
6
5
4
3
3
3
4
4
3
3
5
5
5
9
15
17
SD
23
20
10
9
6
6
3
3
3
3
3
4
3
3
8
7
8
9
14
17
X
37.1
14.1
6.6
4.6
3.8
3.9
4.0
5.8
3.7
6.4
6.8
6.8
5.1
5.4
5.6
5.0
5.6
5.2
5.5
7.6
SD
13.7
6.0
2.3
2.2
2.0
2.0
2.2
3.8
3.1
8.4
8.5
9.3
7.8
8.9
8.2
6.4
5.9
7.7
7.0
8.5
X
5.9
5.8
5.8
5.8
5.8
5.8
5.8
5.8
5.8
6.0
6.0
5.9
5.7
5.6
5.4
5.4
5.4
5.5
5.6
5.9
SD
0.5
0.8
0.8
0.7
0.7
0.7
0.7
0.7
0.6
0.6
0.7
0.9
0.9
0.9
1.0
1.1
1.1
1.3
1.4
1.1
* Mean of 7 sites (see Table 2)
** Standard deviation.
-------
Table 17. MEAN AND STANDARD DEVIATION FOR EXTRACTABLE AND SOLUBLE NUTRIENT CONTENT OF
SOILS FROM MUSKEGON SPRAY AREA AFTER EIGHT INCHES OF EFFLUENT GRANBY SAND.
NO 3
K
Ca
Na
PH
Depth
cm
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
244-259
259-274
274-290
290-305
X*
3.4
2.0
1.1
1.1
1.1
1.1
1.0
2.4
4.1
1.4
1.1
.9
1.7
.9
1.1
.8
.9
1.4
.9
1.1
SD**
3.9
3.3
1.5
1.1
.9
.7
.8
4.3
9.1
1.2
.6
.7
2.0
.6
.8
.7
.8
1.4
1.0
1.1
X
7.6
10.7
6.7
5.0
3.5
3.2
2.1
2.1
2.0
1.8
1.8
1.6
1.9
1.7
2.1
2.1
1.5
1.6
1.7
1.7
SD
9.5
16.7
8.6
5.4
3.8
2.8
2.4
2.0
2.4
1.8
1.5
1.2
1.8
1.8
2.5
2.2
1.4
1.6
2.0
2.5
X
28
16
7
9
10
13
12
12
10
10
8
8
9
9
9
9
8
8
8
9
SD
28
22
7
8
9
14
13
12
9
9
8
8
8
8
8
8
7
6
6
6
X
57
37
26
13
11
9
8
9
8
8
8
9
9
8
8
7
9
8
9
8
SD
ppm
36
30
25
4
5
5
6
5
4
4
3
4
4
4
3
2
6
4
4
5
X
940
940
920
720
570
550
440
560
670
680
630
650
630
510
570
550
570
600
530
580
SD
810
880
670
730
720
690
580
640
660
640
640
700
680
640
650
590
620
620
550
580
X
130
130
91
85
65
45
26
26
17
23
28
37
37
14
37
38
45
45
45
47
SD
100
110
70
83
76
56
26
23
13
17
31
45
45
12
58
64
76
66
63
68
X
88.0
50.8
32.9
24.9
17.5
10.4
7.6
10.8
9.5
11.5
12.3
17.3
13.9
11.9
12.7
10.8
13.9
10.5
9.8
12.8
SD
45.8
23.2
37.6
32.1
18.6
7.3
6.9
7.1
6.6
6.5
6.8
17.0
8.8
8.0
7.9
7.1
12.9
6.1
7.4
8.8
X
6.5
6.1
1.6
6.6
6.6
6.6
6.1
6.7
6.8
7.0
7.2
7.0
7.0
6.9
6.6
6.7
6.6
6.7
6.7
6.7
SD
.7
.8
1.1
.9
1.2
1.4
2.7
1.7
1.7
1.4
1.1
1.3
1.4
1.5
1.6
1.8
2.0
1.9
2.0
1.9
* Mean of 8 sites (see Table 2).
** Standard deviation.
-------
Table 18. "AMMONIUM CONTENT OF SOIL FROM SITE 01.
(CIRCLE 5) AS COMPARED TO THE AVERAGE
OF THE REMAINING SEVEN RUBICON SITES
Depth
COT
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
244-259
259-274
274-290
290-305
Fourth
Mean for
Seven Sites
•
1.52
.75
.64
.61
.32
.24
.33
.27
.32
.32
.32
.30
.39
.21
.35
.24
.45
.35
.37
.49
Sampling
Site
01
ac WH. — —
40.3
30.1
5.3
40.5
2.1
33.5
47.6
40.3
1.1
.24
27.9
9.9
7.6
1.4
11.9
1.6
1.7
35.9
40.0
9.9
35
-------
but the concentrations in these bands were generally low. Rubicon
and AuGres contained less than 1 ppm N as NO., generally, which, if
converted to ppm in solution for 15% moisture in the profile, would
be less than 6 ppm N in solution. The Roscommon sand did show bands
of N07 in the range of 3 to 5 ppm N in the soil (20 to 30 ppm N in
solution at 15% moisture). Site 16 had 56 ppm N as NOo between the
depths of 46 and 107 cm and about 45 ppm N as NOo between 213 and 244
cm in the spring 1975 samples. This was an extremely high NO-j content
in solution. Since this concentration exceeds the quantity of NO-j
reported in the wastewater, it suggests that the source is breakdown
of soil organic matter.
The Granby sites tended to be higher in NO^ content. This may be
attributed to two factors: 1) the high organic matter content of the
surface soil is yielding NH,+ ions through ammonification and later
NOo by nitrification; 2) these sites generally have received lower
applications of wastewater so they have not come to equilibrium with
the NO^ being removed by leaching.
It must be noted here that the samplings for this study were made in
early June and late September, outside of the period during which
corn is actively and rapidly adsorbing N07 from the soil; consequently,
higher levels of NOo were observed here than would be expected during
July or August. Nonetheless, the concentration of NO^ of the Roscommon
and Granby soil profiles would suggest some loss of NO^ at levels in
solution greater than would be desired. The Rubicon and AuGres sites
have lower levels. In view of the level of NOo in the wastewater being
applied (i.e., approximately 4.5 ppm N during the 1974 and 1975 season
except when supplemented by N during the peak portion of the growing
season), one must conclude that the source of the N07 in the profiles
from Roscommon and Granby is from the soil. This should then reduce
in level as the system stabilizes. It does also suggest that the system
as operated at the present time would be incapable of removing higher
levels of NOo if it were in the wastewater since the system was not
capable of removing NO^ generated by the soil. Thus, one would need
to look for N removal in the lagoon system or a cropping system that
is capable of NO- removal during a greater portion of the growing season.
CALCIUM, MAGNESIUM, SODIUM, AND SODIUM ADSORPTION RATIO (SAR)
During the first two years of operation the content of the wastewater
with respect to bases was quite stable as shown in the following table.
36
-------
Table 19. AVERAGE CONTENT OF WASTEWATER IN THE LAGOONS AT MUSKEGON
WASTE TREATMENT FACILITY (DATA FROM DEMIRJIAN, 1975, 1976),
Nutrient 1974 1975
Na
Ca
Mg
K
115*
62.5
16
9
- - HHIII ---------
145*
65
15
10
* The 1974 figure is an average of 85 ppm Na for the west lagoon and
145 ppm for the east lagoon; the 1975 figure is an average of 125
ppm Na for the west lagoon and 164 ppm Na for the east lagoon.
This wastewater was much higher in Na than would normally be en-
countered in soil solution. When such wastewater is passed through
a soil, by the process of cation exchange the soil will come to a stable
equilibrium with respect to the exchangeable bases. If the exchangeable
Na percentage becomes too high, the Na ion which is highly hydrated
dispenses soil clays and organic matter, and the soil structure may
deteriorate. This leads to reduced infiltration rates, poor aeration,
and difficulty in management of the agronomic aspects of the system.
There have been a number of cation exchange equations used to estimate
the quantity of exchange that may occur under this type of situation
(see Fried and Broeshart, 1967). No single equation has proved suitable
for all soil types. Exchange constants for a given soil should be
determined experimentally. Sodium adsorption ratios (SAR) have been
particularly useful in estimating the exchangeable Na under conditions
of irrigation.
The following is an example of the calculation of SAR for 1975:
me/1)
SAR
DriA.
p— _ / 1 i / -i ^^
|Ca me/1 + mg me/1 I
L 2 -J
145 mg Na/1
SAR 19?5 23 mg Na/me =4.46
I" 65 mg Ca/1 + 15 mg Mg/1
20 mg Ca/me 12 mg Mg/me
L 2
The SAR value for the water in 1975 is 4.46 which may lead to exchange-
able Na percentages of 5.5 percent (USDA Handbook 60, 1954). Again
it must be cautioned that the value of 5.5 is strictly an estimate
37
-------
and that evaluations for the particular soils in question could lead
to different values. It is normally estimated that serious difficulties
will arise if exchangeable Na exceeds 15%, thus 5.5 is well below this
value and should give little trouble in these sandy soils.
The question may be posed, "How much Na could be allowed in the waste-
water at Muskegon before serious difficulty is encountered with the
agronomic aspects of the land treatment site?" The conditions that
should be met for safe irrigation is an SAR less than 15 (and less than
7.5 is better) and the conductivity of the water should be less than
2,200 u mhos/cm. Using the 1975 lagoon levels for Ca and Mg an SAR of
7.5 would be reached at 260 ppm Na in the water. It is also estimated
that approximately 400 ppm Na would be required to give a conductivity
of the water equal to 2,200 u mhos. Using these two values, it would
appear that the concentration of Na in the water could be safely in-
creased to 260 ppm Na or even 300 (as an average rounded number). But
values exceeding this should be avoided.
Cation Exchange Capacity
Cation exchange sites in the sandy soils on the Muskegon land treat-
ment facility are expected to arise from the small amount of clay in
the soils and from the organic matter in the surface layers. The clay
content of these soils is extremely low; consequently, the total number
of exchange sites from clay will be very low (probably less than 2
me/100 g soil unless a clay lens is encountered). On the other hand,
the organic matter content of the surface soils can be quite high in
certain areas, particularly for the Granby soils. Thus, the surface
soil of the Rubicon may be expected to have up to 4 me/100 g soil of
exchange sites from organic matter, and the Granby soils might have
as high as 14 me/100 g soil of exchange sites from organic matter.
Furthermore, the exchange sites from organic matter are expected to
be pH dependent; consequently, the rather acid conditions, particularly
for the Rubicon soil, would effectively reduce the cation exchange
capacity to even lower values since the carboxyl groups, clay and or-
ganic matter, would be occupied with H"*" at pH values less than 4 to 5.
Clearing the areas and preparing the land for cultivation has led
to non-uniformity of organic matter content in the surface of the soil.
This may be expected to produce very heterogeneous cation exchange
systems in the surface layers. The areas will become more homogeneous
with time due to mixing through cultivation and to incorporation of
organic residues into the surface soils.
Background Levels of Exchangeable Bases
The Na content of all soils was low and rather uniform throughout
the profile (see tables 5 to 8). Except for the surface soils, the
content was about 0.04 me Na/100 g soil. The only significant devi-
ation from this quantity was in the surface soils from the Granby series
38
-------
which contained about double or 0.09 me Na/100 g soil.
The Mg content of the Rubicon soils was extremely low (Table 5). The
mean of 8 ppm Mg would not be adequate for corn production without
additional Mg. This low content is related to the very acid pH of
the Rubicon sand which has developed because of coniferous forest and
a well-drained sand soil which has led to the removal of Mg by leach-
ing. This is aided by the reduced cation exchange capacity due to
the acid conditions.
The Mg content of the AuGres sand soils (Table 7) is adequate for crop
growth on the average with only site 22 (circle 20) being deficient
in Mg. Again this low value of Mg (less than 10 ppm Mg) was associ-
ated with acid conditions.
The Mg content of the Roscommon soils (Table 6) was similar to the
AuGres except for higher values in the lower layers. In the AuGres
soils the average values were generally less than 10 ppm Mg below 45
cm (18 inches), but the values were generally between 20 and 30 ppm
Mg in the Roscommon soils.
The Granby soils (Table 8) contained considerable Mg in the surface
layers; in fact, the average was above 100 ppm Mg for all layers down
to a depth of 152 cm. These soils were higher because of higher cation
exchange capacities associated with higher organic matter contents
and higher soil pH's in the surface layers. Furthermore, several of
the Granby sites gave evidence of having received applications of dolo-
mitic limestone in the past during a farming operation.
Changes in Exchangeable Bases with Application of Wastewater
The Na content of the soil profiles increased with increasing appli-
cation of wastewater. This is illustrated in table 20 for site 01
(circle 5, Rubicon). The Na extracted by ammonium acetate was below
10 ppm in all layers of the soil prior to application of wastewater.
After application of 20 cm (8 inches) of wastewater, the Na content
of the surface layer was more than 20 ppm, but after the application
of 380 cm (150 inches) of wastewater the Na extracted had increased
throughout the entire profile. In general, water soluble Na will be
much lower than the exchangeable; however, for the sandy Muskegon soils
the low cation exchange capacity of the subsurface layers together
with the high water content (about 15 to 20 percent moisture) makes
it possible for a considerable portion of the Na to be in a water
soluble form and not exchangeable.
This system is rapidly expected to overload with Na during the appli-
cation of wastewater. If we assume a uniform cation exchange capacity
of 2 me/100 g (perhaps high for all but the Granby soil) and a final
exchangeable Na percentage of 5 percent (just slightly higher than
predicted by SAR), we can predict that the profile would hold 900 kg
of Na per ha.
39
-------
Table 20. SODIUM, CALCIUM AND MAGNESIUM CONCENTRATIONS IN THE SOIL PROFILE OF
SITE 01 (CIRCLE 5) AS A FUNCTION OF EFFLUENT APPLICATION.
Effluent Applied Cm *
Depth
cm
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
244-259
259-274
274-290
290-305
0
5.9
5.4
5.5
5.6
5.6
4.8
4.4
4.3
4.6
5.6
3.8
4.7
5.2
6.5
6.8
5.6
4.4
8.1
5.7
7.4
20
22
9.5
5.0
3.5
2.5
2.3
1.8
3.3
1.5
2.0
2.0
1.3
2.8
2.3
2.5
1.3
1.5
2.0
2.7
3.0
380
51
55
54
38
32
25
22
21
23
24
27
28
23
21
22
22
18
20
22
26
0
61
22
13
11
7
7
6
6
6
6
13
7
7
11
22
16
34
75
62
62
20
— ppm Cs. —
40
12
13
1.8
1.8
1.3
1.3
2.8
5.0
0.9
0.4
*
22
12
22
21
21
22
15
44
380
380
230
170
110
67
44
33
33
60
56
35
56
54
54
53
57
40
41
60
153
0
4.7
2.1
1.4
1.5
.5
.2
.1
.1
.4
.2
1.1
.6
.5
1.2
2.7
2.3
5.0
13
9.6
12
20
ppm Mg —
9.4
2.2
1.6
1.0
1.0
1.0
0.8
0.7
0.7
0.7
1.0
0.9
1.0
1.2
1.2
0.3
0.4
0.8
5.3
6.2
380
120
64
61
39
22
14
7.8
8.0
7.6
7.2
9.6
6.9
7.5
8.1
6.6
7.0
6.4
6.5
9.6
8.1
* 0, 8 and 150 inches, respectively.
-------
Example of calculation:
2 me CEC/100 g (5% Na)xlO = 1 me Na/1000 g soil.
1 me Na/1000 g x 23 mg Na/me = 23 mg Na/kg soil.
1 ha = 10,000 sq meters = IxlO8 cm2.
1 ha to a depth of 300 cm = 3.0 xlO10 cm3.
Total weight of soil is 1.3 gm/cm3 x 3.0 xlO1^ = 3.9xl010 gm.
3.9xl010x lxlO~3kg/g x 23 mg Na/kg soil x 10~6 kg/mg = 900 kg Na/ha.
This quantity of Na is furnished by 2.53 x 106 kg (5.58 million pounds)
of water containing 165 ppm sodium. Consequently, an application of
60 cm (24 acre inches) would be expected to saturate the soil with Na
and then to pass most of the Na directly to the drainage water. This
conclusion is verified by the experimental data and suggests that much
of the Na being measured in the lower portion of the profile is in
fact in solution. The final consequences of this should not be serious
since Na is not a real hazard to most crops at the concentration in
the incoming water. Also, Na is not apparently a real pollution hazard
in rivers and lakes at this concentration, but it must be emphasized
that these soils will reach a rapid equilibrium with the incoming level
of Na and any changes in this level will be transmitted to the drainage
water after as little as 50 cm (20 acre inches) of irrigation.
Exchangeable Ca (Table 20) increased considerably in the surface layers
after application of wastewater, but the relative portion of Ca to
other bases decreased considerably as shown by table 20. Thus, before
application of wastewater, the 0 to 15 cm layer contained .3 me Ca/100
gram soil which represented 80 percent of the .38 me bases/100 g soil.
After application of approximately 380 cm (150 inches) of wastewater,
the quantity of Ca had increased to 1.87 me Ca/100 grams but now was
only 62 percent of the bases. This occurred because of the increase
in soil pH from 5.1 to 6.6 during the application of wastewater which
resulted in an increase in cation exchange capacity, most probably
from dissociation of carboxyl groups associated with soil organic matter.
This increase in cation exchange capacity will allow the soil to hold
more exchangeable bases. As with Na, it must be concluded that after
application of no more than one year's wastewater, the soil will be
at equilibrium and the composition of the incoming wastewater will
be very similar to the composition of the water being discharged from
the drainage system. Again there should be no hazard to either agro-
nomic crops or surface waters from this input of Ca.
The Mg content of the soils (Table 20) has rapidly increased from the
deficient levels on the Rubicon soil to levels that would be adequate
for crop growth as a result of wastewater application. The fraction
of the exchangeable bases that was Mg increased during the application
of wastewater. For example, site 01 contained 0.039 me Mg/100 grams
before application of wastewater which was 10 percent of the bases;
after application of 380 cm (150 inches) of wastewater, the magnesium
content increased to 1.0 me Mg/100 grams which was now 33 percent of
the bases. Again this is expected to stabilize at a level controlled
41
-------
by the ratio of Mg to other bases in the applied wastewater and should
not be detrimental to agronomic crops or to surface waters.
PHOSPHORUS
Both total and Bray PI extractable P (an index of P available to crops)
have been measured in the profile samples. The background data (tables
5 to 8 and 9 to 12) were obtained by the same combination of profile
samples as outlined under the N section.
Effect of Soil Type on the Initial Phosphorus Content of Soil Profiles
Rubicon sand profiles were initially moderately high in available
P. This was true to a 122 cm (48 inch) depth indicating that the P
content of the parent material was relatively high. The quantity of
25 ppm P in the surface soils should be adequate for agronomic crops
(particularly corn) in the initial years of the operation.
Both AuGres and Roscommon sands were much lower in P initially as
compared to the Rubicon profiles. The mean values of 9.6 and 11.5
ppm P for Roscommon and AuGres, respectively, may be deficient for
maximum corn production during the initial years of operation. Generally
speaking, wastewater should supply adequate P for growth of the agro-
nomic crop so that this low value should not be a problem, but the
wastewater being applied at Muskegon is relatively low in P and was
particularly low during the first year. Consequently, it may take
a few years before these soils become totally adequate for maximum
crop production. But the addition of P fertilizer would not appear
to be justified since that would result in shortening the number of
years that the site will effectively remove P.
The Granby sand profiles have a mean value of 17.8 ppm P, but they
have a much higher standard deviation. It appeared that certain of
the Granby sites (for example, 07 in circle 46 and 26 in circle 41)
had been previously farmed and fertilized. The level of P fell to
low levels in these soils after the 30 cm (12 inch) depth. Certain
of the Granby sites were very low in P initially, indicating that when
they had not been fertilized, their P level was equal to or lower than
AuGres or Roscommon sands.
Phosphorus Adsorption Maximum for the Major Soil Types
It was not within the scope of this project to determine or estimate
the P adsorption capacity of these soils, but nevertheless, 8 samples
were selected from the first sampling period and the P adsorption capa-
city estimated by the Langmuir adsorption isotherm (Ellis, 1973).
This data is given in table 21. These sands have a moderately low
P adsorption capacity. The Rubicon sand is the highest, the AuGres
and Roscommon sands intermediate, and the Granby sand extremely low.
It should also be noted that the AuGres sand had a very low K value
(bonding energy), the sigificance of which will be discussed in a
42
-------
Table 21. PHOSPHORUS ADSORPTION CAPACITY OF SELECTED SAMPLES
FROM MUSKEGON WASTEWATER FACILITY.
Soil
Series Site
Rubicon (01)
AuGres (03)
Roscommon (23)
Granby (24)
, , . Soil Content of
Adsorption* _ ,, „ _ . „ .,
„ , ., . „.,., P @ 3 ppm P in Soil
Depth Maximum K** _ ,
Solution
cm
0-15
15-30
0-15
15-30
0-15
15-30
0-15
15-30
ppm
160
158
115
175
137
114
42
23
xlO l
5.6
25.0
1.3
0.3
5.0
14.6
7.3
4.3
ppm
134
151
64
40
113
106
37
19
Quantity of P that will be adsorbed by the soil with maximum P in
solution (as predicted by Langmuir Adsorption isotherm).
kit
K is a constant from the Langmuir that is related to bonding energy.
43
-------
later section. With this limited number of samples it cannot be certain
if the Granby sample is representative or if the adsorption capacity
for P would increase in the lower horizons. Prior experience has shown
that horizons high in organic matter are generally low in P adsorption
capacity and that the adsorption capacity increases in the subsoil
layers.
The Relationship Between Phosphorus and Agricultural Production
The levels of P needed in soils for agronomic production depends upon
the yield goal or level expected. For the Muskegon area the maximum
yield that should be expected is probably near 121 q/ha (150 bu/acre)
for corn. This is due to very sandy, low productive soils and climate.
In the initial years of operation of the site a 80 q/ha (100 bu/acre)
yield goal may be more realistic. Twenty to 30 ppm extractable P would
be adequate for 80 q/ha and 30 to 40 ppm P would be adequate for 121 q/ha.
As pointed out earlier, only the Rubicon soils are adequate at the
present time, with the exception of those soils that had a previous
history of fertilization. It is expected that the P in the wastewater
will increase the soil level so that in a few years all soils will
be adequate.
One of the major objectives of the land treatment system is to produce
clean water through nutrient removal by crops or by adsorption by land.
Phosphorus removal by land treatment is an example where both methods
operate. Phosphorus is first expected to be adsorbed by the soil par-
ticles, but much of this P is left in a state that is available for
plant growth. Therefore, the soil may accumulate P during late fall
and early spring when no crop is growing and make it available to the
crop when needed. Total removal of P by a corn crop is expected to
be from 16 to 25 pounds per acre (18 to 25 kg/ha) depending mostly
upon final yield (See Appendix III). The quantity of wastewater neces-
sary to supply 16 pounds of P (18 kg) will be 36 ha-cm (35 acre-inches)
containing 2 ppm P; 23.7 ha-cm (23 acre-inches) containing 3 ppm P;
or 17.5 ha-cm (17 acre-inches) containing 4 ppm P. Although the content
of the wastewater is at the lowest level at the present time, it may
likely increase to between 3 and 4 ppm P in the futu."ۥ.. Consequently,
the needs of the crop will easily be met and exc.ess P will be supplied
to the soil.
Phosphorus Adsorption by Soils after Application of Wastewater
The soils may be roughly divided into three groups based on the quantity
of wastewater applied during the first two years—those receiving 50
to 178 cm (20 to 70 inches), those receiving from 254 to 330 cm (100
to 130 inches), and those receiving greater than 380 cm (150 inches).
Assuming a P concentration of 2 ppm in the wastewater, the P added
with the wastewater would thus vary from a low of approximately 10
pounds per acre (llkg/ha) to a high of nearly 80 pounds per acre (90
kg/ha). Due to the non-random nature of the location of the soil types,
the Rubicon sands all received nearly 80 pounds of P/acre (90 kg/ha);
44
-------
whereas, the Granby sites received approximately 20 pounds of P/acre
(22 kg/ha). AuGres and Roscommon were intermediate, receiving averages
of 43 and 35 pounds of P per acre, respectively (43 and 39 kg/ha).
Therefore, it is difficult to compare the different soil types as to
removal of P. A site-by-site comparison showed that 6 of the 8 Rubicon
sites had accumulated P in their surface layers; one site was too vari-
able to draw a meaningful conclusion; and one showed no accumulation.
Table 22 illustrates the type of data that were obtained for the Rubicon
sand profiles.
The quantity of P accumulated in the surface two layers may be estimated
by the following calculation:
(1) Weight of soil in a 15 cm layer of one hectare is equal to the
bulk density (1.3 gm/cm) times the volume of soil (1 x 10" sq cm/ha
x 15 cm depth) = I,950xl06 gm = 1.95xl06 kg soil/ha.
(2) P adsorbed in the 0-15 cm layer = 38-21 = 17 ppm P.
17 kg P
(3) 17 ppm P = Ixlo6 kg soil x l-95xlOb kg soil = 33.1 kg P.
By a similar calculation, the P adsorbed in the 15-30 cm layer is:
10 k|f f _ x 1.95xl06 kg soil = 19.5 kg P.
Ixl0b kg soil
The total P adsorbed in the surface two layers would be approximately
53 kg P.
Considering that about 70 kg of P per ha were applied and that crop
removal during the two years could be expected to be no more than 22
kg P per ha (since the yield was very low the first year), this balance
is within experimental error and would suggest that only trivial amounts
would have passed through the Rubicon sands into the drainage water.
The exception to the Rubicon data was site 12 located in circle 22.
This site showed no accumulation of P. In addition, examination of
the sodium data suggests that it did not receive as much wastewater
as indicated in records. The reason for this is not known, but it
could possibly have occurred due to non-uniform application of the
wastewater on the field with higher application at locations other
than that sampled. The potential effects on soil and drainage water
of non-uniform application of wastewater will be discussed at a later
time.
With the AuGres sites it is difficult to ascertain any accumulation
of P in the profiles. Characteristically, they have increased levels
of P at lower depths in the profiles in the background samples. This
zone of accumulation appeared to vary in depth over rather short dis-
tances as judged by the different samplings. Table 23 gives a compari-
son of background P and the level after the application of approximately
380 cm (150 inches) of wastewater for site 04 (circle 24). Site 04
45
-------
Table 22. INCREASE IN EXTRACTABLE P AFTER APPLICATION OF
380 cm OF WASTEWATER TO RUBICON SAND, SITE 02 (CIRCLE 8).
Depth
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
Extractat
Background *
- ppm
21
16
20
30
38
24
20
21
>le P
Fall 1975
38
26
18
19
44
34
21
17
* Mean of 1st, 2nd and 3rd Samplings
from Summer 1972 through Fall 1973.
46
-------
Table 23. CHANGE IN EXTRACTABLE P AFTER APPLICATION OF 380 cm OF
WASTEWATER TO AUGRES SAND, SITE 04 (CIRCLE 24).
Extractable P
Depth
cm
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
Background*
Ppm
5.8
4.1
4.2
7.1
14.6
16.4
11.6
10.3
12.5
12.4
13.6
11.4
8.6
8.1
Fall 1975
—
11.3
4.4
6.8
10.8
5.2
5.6
14.2
22.3
15.3
13.2
10.2
7.6
7.0
5.6
ppm
5.5
.3
2.6
3.7
( 9.4)
(10.8)
2.6
12.0
2.8
.8
( 3.4)
( 3.8)
( 1.6)
( 2.5)
Net Change
Kg/ha-15cm **
10.7
.6
5.1
7.2
(18.3)
(21.1)
5.1
23.4
5.5
1.6
( 6.6)
( 7.4)
( 3.1)
( 4.9)
* Mean of 1st, 2nd and 3rd Samplings from Summer 1972 through Fall
1973.
** Assuming a bulk density of 1.3 gm/cc.
47
-------
data, showing no P accumulation in the soil profile, is representative
of AuGres sandy soils measured at each of the four sites (03, 04, 05,
22) receiving greater than 320 cm of water. The remaining three sites
(25, 33, 34) received less than 170 cm of water and showed no accumu-
lation of P in the soil profile. Although there is a slight increase
in the P content of the surface layer, it is probably within the ex-
perimental error and in no way accounts for the approximately 50 pounds
per acre of excess P (56 kg/ha) applied to this site. If the change
in P is accumulated through the 213 cm depth, there is no net change
suggesting that all changes are within experimental error. This must
then suggest that P is moving through this profile. This may, in fact,
agree with the data for the adsorption isotherms in that the bonding
energy for P adsorption in the AuGres soils was extremely low, giving
rise to movement at low levels of P in solution.
Life of Site for Phosphate Removal
The data is too preliminary at this time to accurately estimate the
life of the site for P removal from measuring profile data, but a
preliminary estimate has been made from the adsorption data. There
are many management techniques that will affect the number of years
that this site will remove P. The discussion below is given to stimu-
late consideration as to these management factors and not with the
idea that the estimates are necessarily accurate. It was assumed in
these calculations that effective drainage is to 152 cm (5 feet) in
all cases, that water is applied at a rate of 152 cm (60 inches) per
year, and that the adsorption capacity is that given in table 21.
The two soils that represented the extremes in P adsorption capacity,
Rubicon and Granby, were selected for examples. From table 24 it is
evident the Rubicon sand is a good soil for adsorbing P, whereas the
Granby adsorbs little P. With the combination of a high yield and
low P input, the life of Rubicon sand in P adsorption is very long.
Increasing the level of P in the wastewater added to the soil decreases
the effective life of the system drastically because crop removal then
no longer represents a major portion of the P removal.
One effective management practice is to increase the yield of
corn. Thus, in the initial year's operation the corn was nitrogen
deficient and yielded little more than 24 q/ha (30 bushels per acre),
but increasing the yield to 80 q/ha (100 bushels per acre) through
good management would increase the period of time that the soil would
adsorb P by 25 or more percent for 2 to 3 ppm P in the wastewater.
Increasing the yield to 121 q/ha (150 bushels per acre) would double
the length of time that the soil would adsorb P at these levels of
P input. (See Appendix III for nutrient content of corn).
The management technique of producing uneven application of wastewater
by allowing it to flow freely through ends of spray bar downspouts
may lead to a much shorter effective life of the system. This is illus-
trated in table 25 where calculations show the effect of putting all
of the water on either 100, 50, or 25 percent of the soil surface.
48
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Table 24. ESTIMATED NUMBER OF YEARS THAT P MAY BE REMOVED
FROM WASTEWATER APPLIED AT 152 cm (60 INCHES) PER YEAR.
Soil Type
Rubicon**
Granbyt
Yield*
q/ha
24
40
80
120
24
40
80
120
bu/acre
30
50
100
150
30
50
100
150
P
2ppm
115
132
216
371
12
14
23
38
Content of Wastewater
3ppm
71
77
100
137
7.5
8
11
14
4ppm
52
56
67
81
5.5
5.9
7.0
8.6
5ppm
41
43
49
56
4.3
4.5
5.2
6.0
* P removed by the crop would be 7.3, 15 and 22 pounds per acre for
50, 100 and 150 bushels yield, respectively.
** The adsorption capacity for Rubicon sand is estimated to be 2,600
pounds P per acre five foot depth; after this quantity is adsorbed
the level in the drainage well approached that added in the waste-
water.
t The adsorption capacity for Granby sand is estimated to be 274
pounds P per acre five foot depth; after this quantity is adsorbed
the level in the drainage well approached that added in the waste-
water.
tt The number of years before sufficient P has been added beyond that
removed by crops to equal the adsorption capacity.
49
-------
Table 25. EFFECT OF UNEVEN DISTRIBUTION OF WATER ON THE EFFECTIVE
LIFE OF P REMOVAL ON RUBICON SAND.
Method of Fraction of the land P level
distribution receiving water 2ppm 3ppm 4ppm 5ppm
Even
Uneven
Uneven
/o
100
50
25
216
67
28
yec
100
39
17
67
28
13
49
21
10
* The number of years is the time required to saturate that fraction
of soil (100, 50, 24 25) with P.
50
-------
Even on the Rubicon soil the effective life of the system could be
shortened to 17 to 28 years if this practice were followed. The level
of P that would result in the drainage water would not be as high as
if the entire soil were saturated—i.e. for a 3 ppm P input level,
the drainage should contain 1.5 or .75 ppm P, respectively, for 25
and 50 percent soil coverage. The result would be an increased level
of P in the drainage beyond a tolerable level in a much shorter num-
ber of years.
Considering the rather drastic differences in ability to adsorb P by
these soils, they should be followed rather closely by soil analyses
and consideration given to applying more water to the Rubicon sand
and the Roscommon sand than to the other two series.
SOIL pH
Since large volumes of wastewater will pass through the soils on the
treatment site, following the law of mass action, soil pH is expected
to be ultimately controlled by the pH of the wastewater applied (i.e.,
7.2 to 7.4); consequently, it is of minor importance to our discussion.
But the soil pH does affect certain of the chemical reactions and thus
should be considered.
Background data
Initially the Rubicon sites (Table 5) were acid throughout the profile
with average pH's in the surface 122 cm (4 feet) between 5.0 and 5.5,
and below this depth the pH ranged from 5.5 to 6.0. The AuGres soils
(Table 7) were between 5.5 and 6.2 throughout the profile. The Roscommon
sands (Table 6) were slightly less acid in the surface 168 cm (5.5 feet).
The Granby soils (Table 8) were much more variable, both in the surface
and in the subsurface layers. First, the surface layers of some lo-
cations have evidence of a prior history of lime application. For
example, site 37 (circle 42) had a pH of 7.3 in the initial sampling,
but site 27 (circle 40) had a pH of 5.3 in the initial sampling. This
illustrates the variation due to prior liming. A second phenomenon
occurred on 6 of the 8 Granby profiles. When samples were removed
and air-dried, the pH of the subsurface layers (generally from 100
to 300 cm) became very acid with pH values from 2.9 to 4.0. This is
not an unusual phenomenon in soils that have been waterlogged for an
extended period of time. Under reducing conditions, SO/~ is reduced
to sulfide and may then accumulate if little leaching occurs. Soil
pH will generally be between 6.0 and 7.0 in the anaerobic condition,
but as soon as the soil is aerated, the sulfide will oxidize to SO^
and generate t^SO^ which leads to very acid conditions. This is ex-
pected to be a temporary condition for two reasons: 1) soils are not
stable at extremely acid conditions and Fe and Al oxides and hydroxides
will decompose by combining H ions with hydroxyls to form water; this
will generally lead to soil pH's between 4.0 and 5.0; 2) the addition
of wastewater with pH of 7.2 to 7.4 and high levels of Ca, Mg and Na
will rapidly lead to increased soil pH's as these cations replace H+.
51
-------
Changes Induced by Drainage
The greatest change induced by agronomic development was the change
in aeration status that occurred with the installation of tile drainage.
The acid conditions encountered in the Granby soils had disappeared
from all sites except site 36 (circle 46) by the fall of 1975. Much
of this change must be attributed to chemical changes in the soil that
occurred because of acid dissolution of minerals, leaching of bases
from surface horizons, and losses of acid materials from the subsoils
through leaching.
Changes Induced by Wastewater Application
The soil pH is increasing rapidly with the application of wastewater.
By fall of 1975 only six sites had pH values below 5.0 in the surface
compared to 11 initially. Thirty sites had pH values greater than
6.0 by fall of 1975 compared to 9 sites initially. All sites had shown
increases in soil pH except site 36 (circle 46), a Granby which had
received low water application.
It was anticipated (and observed in the field personal communication
from Dr. Demirjian) that the installation of drainage in the Granby
soils would lead to loss of iron in the drainage water. As previously
explained, aeration of a soil that was previously waterlogged many
times leads to the production of H^SO^. This reduces the soil pH and
dissolves Fe oxides and hydroxides. The water draining from such an
area will then contain Fe in either ferrous or ferric state of oxida-
tion. Characteristically, the drainage water which is initially clear
will form a white to gray colloidal precipitate upon exposure to other
water with a higher pH and to the air. This precipitate will turn
to yellow and then to red upon oxidation. It is expected that this
effect is caused by drainage and not by application of wastewater.
Once the pH of the soil profile is increased, due either to the ap-
plication of wastewater or to chemical reactions within the profile,
this loss of Fe should be eliminated.
TOTAL CARBON
The total C content of the Rubicon sand profiles was quite low initially,
the AuGres slightly higher, the Roscommon sands about fifty percent
higher, and the Granby sands were very high in organic C (0.93, 1.14,
1.48, and 3.21% C, respectively, for Rubicon, AuGres, Roscommon, and
Granby). The organic matter content of the Rubicon sands decreased
rapidly with depth in the 15 to 30 cm depth (6 to 12 inch), but the
other soil series did not show such a dramatic decrease. The variation
in total C content between samplings was very large, which is expected
because of the clearing and deep discing in the initial establishing
of the farming operation.
There were no obvious changes in the organic C content after application
of wastewater. It would be anticipated that the Granby soils would
52
-------
decrease in organic matter content during the first five or ten years'
operation mainly due to the increased aeration. Since the surface
of the other soils was well aerated initially, they should not under-
go this change. The organic matter content of the wastewater is suf-
ficiently low that it is not expected to affect the organic C content
of the soils. Application of sludge could increase the organic matter
content of these soils.
Agriculturally, the Rubicon, Roscommon, and AuGres sands could benefit
from additional organic matter. This suggests that applications of
sludge could be quite beneficial in crop production.
POTASSIUM
Although K is not normally of concern from a pollution viewpoint,
it is of importance in agronomic production and, therefore, indirectly
affects the ability of a land treatment system to remove nutrients
by the action of a biological filter. Also, K does move in sandy soils
and, consequently, may be expected to be leached under a land treatment
system.
Background Data for Potassium
Data for ammonium acetate extractable (exchangeable) K are summarized
in tables 5 to 8. Rubicon sand (Table 5) was initially very low in
K with only 21 ppm average in the surface soil and decreasing to less
than 5 ppm in many of the subsurface layers. This level is not ex-
pected to be adequate for crop growth without supplemental K. The
wastewater contains about 2.34 kg K per ha-cm (2.27 pounds/acre-inch)
of effluent; therefore, an application of 150 cm (60 inches) of waste-
water per year should be adequate for crop growth. Although they would
still be considered low, the Roscommon and AuGres soils (Tables 6 and
7) contained about 50 percent more K in the surface than did Rubicon.
Both soils were still very low in the subsurface layers. The Granby
soils (Table 8) averaged 84 ppm K in the surface layers, undoubtedly
reflecting a prior farming history.
Changes Induced by Wastewater Application
Table 26 summarizes changes in soil K with application of wastewater.
Essentially the Rubicon, Roscommon, and AuGres soils show no change
in K status after application of wastewater. This would suggest that
the quantity being applied is approximately that being removed by crops
or that K is being leached through the soil profile. Eighty quintal
per hectare (100 bu/acre) of corn would be expected to remove 21 kg/ha
(19 pounds/acre) of K (Ellis, et al. 1973). But many of the sites
had received more than 140 kg (125 pounds) of K per year applied in
the wastewater. Since it was not recovered in the soil, this would
suggest that it was being lost in the drainage water. Data by Demirjian
(1975) shows 3 and 6 ppm K in the tile and discharge water, respectively,
confirming that considerable K is being discharged from the site.
53
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Table 26. AMMONIUM ACETATE EXTRACTABLE K AT
VARIOUS SAMPLING PERIODS*.
Sampling Period
Soil Type
Rubicon
Rosconnnon
AuGres
Granby
Depth
cm
0-15
15-30
106-122
0-15
15-30
106-122
0-15
15-30
106-122
0-15
15-30
106-122
Bkg
21
13
7
33
17
7
32
21
5
84
37
7
1974
32
21
6
25
19
6
33
16
4
57
37
9
Spring 1975
31
18
7.8
25
16
7.8
30
24
5.7
46
30
10
Fall 1975
22
13
4.4
29
19
4.4
28
20
6.5
30
23
7
* Bkg is a average of the first three sampling periods prior to
application of wastewater, 1974 is an average of locations within
each soil type after 8 inches of application, and the remaining
two sampling periods are an average of all sites for each soil
type even though water distribution was not uniform.
54
-------
Loss of the monovalent ion K in the drainage water occurs because it
does not compete favorably with divalent ions, particularly Ca, for
exchange sites. Thus, when wastewater is applied that contains 3.25
m.e./liter Ca but only 0.25 m.e./liter K, it is most likely that a
large percent of the K will be lost by leaching.
TOTAL SOIL ANALYSIS
Total soil chemical analysis showed little change during the period
of wastewater application except for changes in total N and C which
were previously discussed. Thus, for the short-run time period it
may be concluded that available and extractable soil chemical analyses
are much more sensitive to changes induced by wastewater application
than total analyses. This would suggest that these are the analyses
that should be followed during the next one to three years. Nonethe-
less, the total chemical analysis data are valuable in establishing
background levels which may be useful for long-term evaluation of the
land treatment system. But it would appear that total analysis made
on an every-five-year basis would be adequate to follow all changes
in total nutrients except N and C.
55
-------
REFERENCES
Demirjian, Y. A., 1975. Muskegon County Wastewater Management System,
Land Treatment of Municipal Wastewater Effluents Design Seminars,
U. S. EPA Technology Transfer.
Demirjian, Y. A., 1976. Muskegon County Wastewater Management System.
Report to EPA.
Ellis, B. G., 1973. The soil as a chemical filter. In: Recycling
Treated Municipal Wastewater and Sludge through Forest and Cropland,
Sopper, W. E. and L. T. Kardos (Eds.). Penn. State Press, Univ. Park,
PA. pp. 46-70.
Ellis, B. G., A. E. Erickson, B. D. Knezek, R. J. Kunze, I. F. Schneider,
E. P. Whiteside, A. R. Wolcott and R. L. Cook. 1973. Land Treatment
of Wastewater in Southeastern Michigan. Detroit Dist. U.S. Army
Corps of Engineers.
Fried, Maurice and Hans Broeshart. 1967. The Soil-Plant System.
Academic Press, New York.
56
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SECTION V
HEAVY METALS
This section gives data and interpretation of the chemical analyses
which were performed on each of the major soil types to establish back-
ground levels of Fe, Mn, Zn, Cu, Pb, and Hg. Changes in the soil's
content of these heavy metals after application of wastewater during
the first two years of operation of the land treatment section of the
Muskegon waste treatment system are reported and discussed. The dis-
cussions are arranged in the following order: general background and
summary; and chelate extractable heavy metals.
GENERAL BACKGROUND AND SUMMARY
Selected total and chelate extractable micronutrients and heavy metal
analyses were conducted on soil profile samples. The elements deter-
mined were Fe, Mn, Zn, Cu, Pb, and Hg on samples taken at 15 cm (6
inch) intervals down to a depth of 305 cm (120 inches) in Rubicon,
Roscommon, AuGres, and Granby sands which are the main soil types on
the wastewater treatment site. Samples were obtained at 8 sites on
the Rubicon sand, 9 sites on the Roscommon sand, 7 sites on the AuGres
sand, and 8 sites on the Granby sand (Figure 1 and Table 2).
Differences in total and chelate extractable Fe, Mn, Zn, and Cu in
the Rubicon, Roscommon, AuGres, and Granby sands varied widely from
sampling site to sampling site even within a soil type. However, general
trends were evident, and the major differences in extractable metals
were between the surface layers and points deeper in the profile.
Also, major changes in extractable metal levels occurred between the
background samples (first three samplings) and the final sampling taken
in September 1975. The background data for extractable heavy metals
is given in tables 27 to 30, and the background data for total heavy
metals is given in tables 31 to 34. Table 35 has been prepared to
compare the changes in extractable heavy metals in the final sampling
with the baseline data at two depths, 0 to 15 era (0 to 6 inches) and
137 to 152 cm (4.5 to 5 feet).
In general, the only metal added to the soils in appreciable quantities
through the wastewater was Zn. Zinc, which may have been added in
amounts up to 0.2 ppm Zn in the wastewater, did not show any total
accumulation, even though more than 6 kg per ha (7 pounds per acre)
of Zn could have been added to sites receiving more than 380 cm (150
inches) of wastewater. Crop removal would account for less than 0.9
kg/ha (1 pound per acre) of Zn. Therefore, Zn should be detected in
the surface samples in the next few years if the level in the irriga-
tion water is greater than 0.1 ppm Zn.
57
-------
Table 27. MEAN AND STANDARD DEVIATION OF EXTRACTABLE HEAVY METALS OF SOILS
FROM MUSKEGON SPRAY AREA-BASELINE DATA RUBICON SAND.
Ol
00
Depth
cm
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
244-259
259-274
274-290
290-305
F
X*
72
36
14
11
6.9
6.1
6.3
5.8
5.7
7
6.6
6.2
6.5
7.1
7.9
7.9
8.3
7.5
8.4
9.1
e
SD**
54
40
8.9
7.1
5.6
4.8
4.5
4.1
3.6
5.2
5.6
4.1
3.7
4.1
6.3
5.4
6.5
6.5
6.9
7.2
X
9
3.2
1.6
1.5
1.2
1.4
1.4
1.4
1.3
1.6
1.3
1.3
1.4
1.4
1.7
1.4
1.4
1.3
1.6
1.6
Mn
SD
11.0
4.4
1.2
1.6
1.4
1.5
1.5
1.4
1.4
2.0
1.3
1.4
1.3
1.4
2.0
1.3
1.3
1.3
1.6
1.7
X
1.70
.59
.60
.27
.23
.26
.24
.21
.23
.34
.20
.24
.25
.27
.43
.26
.25
.26
.23
.41
Zn
SD
1.58
.32
.85
.18
.16
.31
.18
.21
.21
.63
.16
.17
.21
.21
.70
.23
.24
.21
.17
.56
X
.30
.27
.22
.18
.19
.17
.23
.16
.16
.19
.24
.21
.15
.17
.17
.22
.23
.22
.20
.22
Cu
SD
.24
.26
.24
.23
.26
.19
.23
.16
.24
.21
.30
.21
.15
.19
.20
.24
.29
.31
.25
.23
P
X
.23
.14
.09
.07
.07
.07
.09
.07
.07
.06
.07
.09
.06
.06
.05
.06
.07
.07
.08
.09
b
SD
.36
.29
.17
.10
.10
.10
.14
.11
.10
.09
.10
.12
.10
.09
.08
.09
.10
.10
.12
.12
X
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
«g
SD
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
* Mean of 8 sites (see Table 2) and 3 sampling dates (7/72, 6/73 and 9/73).
** Standard deviation.
-------
Table 28. MEAN AND STANDARD DEVIATION OF EXTRACTABLE HEAVY METALS OF SOIL FROM
MUSKEGON SPRAY AREA-BASELINE DATA ROSCOMMON SAND.
Fe
Mn
Zn
Cu
Pb
Kg
Ul
VO
Depth
f*rn
V^IU
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
244-259
259-274
274-290
290-305
X*
107
73
32
21
23
13
14
14
16
18
18
21
20
19
18
14
18
15
14
14
SD**
60
48
24
14
29
7
12
9.6
12
16
13
15
17
18
15
10
12
9.6
10
14
X
2.9
1.7
1.1
.9
.7
.7
.9
.8
.9
1.1
.9
.9
1.0
1.2
.9
.9
1.1
1.0
1.0
1.2
SD
2.3
1.3
1.3
1.2
1.0
1.1
1.8
1.2
1.2
1.8
1.1
1.3
1.6
2.3
1.3
1.5
2.0
1.7
1.4
2.1
X
1.73
1.08
.61
.42
.38
.42
.40
.42
.48
.50
.58
.70
.94
.52
.52
.48
.50
.56
.48
.50
SD
- ppm —
.86
.53
.41
.31
.24
.35
.29
.38
.45
.42
.42
.95
.99
.36
.34
.36
.35
.62
.37
.38
X
.39
.33
.28
.27
.26
.25
.28
.35
.40
.49
.42
.31
.32
.32
.36
.31
.32
.31
.33
.37
SD
.22
.21
.22
.21
.25
.18
.21
.26
.30
.40
.36
.27
.28
.23
.25
.21
.26
.21
.27
.26
X
.42
.24
.07
.09
.08
.09
.07
.08
.07
.07
.08
.11
.08
.09
.09
.07
.08
.07
.06
,06
SD
.67
.47
.12
.13
.12
.15
.10
.12
.12
.12
.12
.23
.12
.15
.18
.11
.15
.09
.10
.09
X
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
SD
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
* Mean of 9 sites (see Table 2) and 3 sampling dates (7/72, 6/73 and 9/73).
** Standard deviation.
-------
Table 29. MEAN AND STANDARD DEVIATION OF EXTRACTABLE HEAVY METALS OF SOILS FROM
MUSKEGON SPRAY AREA-BASELINE DATA AUGRES SAND.
Depth
cm
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
244-259
259-274
274-290
290-305
Fe
X
77
47
27
27
25
28
23
28
29
26
22
18
22
23
23
22
21
21
22
23
SD
43
31
19
29
25
18
15
37
40
24
23
18
18
19
18
16
15
13
15
18
Mn
X
2.9
2.2
1.5
.9
.9
.9
.9
.9
.8
.9
.9
.9
.8
.9
.9
.9
.9
.9
.9
.9
SD
2.1
4.4
2.8
1.4
1.4
1.5
1.4
1.4
1.4
1.4
1.4
1.4
1.5
1.4
1.5
1.4
1.4
1.5
1.5
1.4
Zn
X
2.06
1.27
.64
.43
.64
.52
.53
.44
.48
.54
.46
.41
.49
.48
.63
1.40
.50
.61
.62
.64
SD
ppm
1.30
1.76
.47
.25
.72
.31
.54
.38
.29
.31
.25
.30
.31
.35
.40
2.35
.25
.35
.35
.46
Cu
X
.42
.23
.19
.16
.15
.15
.14
.25
.21
.22
.20
.22
.20
.23
.22
.24
.24
.16
.16
.19
SD
.56
.22
.21
.17
.17
.21
.14
.25
.21
.18
.18
.21
.17
.21
.20
.22
.21
.15
.13
.16
PI
X
.94
.19
.15
.10
.11
.11
.10
.10
.18
.13
.13
.11
.10
.13
.13
.15
.16
.13
.11
.14
5
SD
1.42
.26
.21
.12
.13
.13
.12
.13
.32
.18
.18
.15
.15
.19
.16
.18
.19
.22
.13
.22
HR
X
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
SD
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
* Mean of 7 sites (see Table 2) and 3 sampling dates (7/72, 6/73 and 9/73).
**Standard deviation.
-------
Table 30. MEAN AND STANDARD DEVIATION OF EXTRACTABLE HEAVY METALS OF SOILS FROM
MUSKEGON SPRAY AREA-BASELINE DATA GRANBY SAND.
Depth
r*Tn
t-lll
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
244-259
269-274
274-290
290-305
Fe
X
163
123
8?
76
74
72
87
106
85
85
93
95
85
81
71
69
64
55
61
54
i
SD
158
78
64
98
98
58
60
85
62
58
80
73
67
69
59
51
50
51
45
43
M
X
2.8
1.6
1.2
1.2
1.1
1.1
.9
.9
.9
.9
1.0
.9
.9
1.1
.8
.9
.9
.8
1.0
.8
n
SD
3.3
1.7
1.4
1.9
1.7
1.7
1.1
1.1
1.1
1.1
1.0
1.1
1.2
1.1
1.0
1.0
1.1
1.0
1.1
1.1
Zr
X
3.08
2.43
.81
.80
.69
.59
.64
.65
.97
.76
.84
1.16
1.12
1.07
.99
.94
.91
.92
1.00
1.13
i
SD
1.74
3.53
.56
1.01
.70
.35
.39
.41
.84
.35
.50
.83
.71
.62
.52
.44
.58
.58
.60
.83
Cu
X
.47
.43
.36
.40
.45
.46
.40
.48
.38
.41
.46
.44
.40
.32
.40
.41
.35
.39
.42
.46
SD
.66
.35
.25
.31
.36
.39
.39
.36
.34
.42
.41
.35
.30
.28
.34
.40
.34
.36
.36
.40
Ft
X
.62
.61
.33
.38
.36
.24
.23
.24
.22
.21
.25
.23
.23
.20
.21
.21
.32
.20
.26
.21
»
SD
.87
1.00
.45
.87
.73
.40
.41
.41
.41
.41
.43
.40
.43
.40
.41
.40
.64
.40
.51
.41
Hg
X
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
SD
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
.00
* Mean of 8 sites (see Table 2) and 3 sampling dates (7/72, 6/73 and 9/73).
** Standard deviation.
-------
Table 31. MEAN AND STANDARD DEVIATION OF TOTAL HEAVY METALS OF SOILS FROM MUSKEGON
SPRAY AREA-BASELINE DATA RUBICON SAND.
Depth
SSfY)
cm
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-383
183-198
198-213
213-229
229-244
224-259
259-274
274-290
290-305
Fe
X
4200
4100
4300
4200
3600
3300
3500
3300
2800
2900
3100
3200
3000
3100
2600
3100
3000
3200
3400
3400
SD
1300
1300
1300
1300
1100
1200
1500
1300
900
900
1100
1300
1200
1100
1300
1600
1200
1600
1600
1500
Mn
X
170
110
82
75
60
60
69
60
59
51
59
60
66
60
68
65
66
65
62
63
SD
90
56
25
24
24
25
32
26
29
16
21
25
39
23
35
36
36
26
26
30
Zn
X
35
33
27
24
22
18
18
18
15
15
17
18
32
19
20
23
26
26
22
46
SD
ppm
17
19
10
9
11
10
10
9
10
11
10
11
69
23
21
23
32
48
23
35
Ci
X
25
22
22
22
20
18
20
20
20
24
24
23
21
20
19
20
21
24
20
20
i
SD
40
34
39
42
38
37
40
38
44
53
59
45
45
44
35
39
43
55
46
41
Pb
X
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
SD
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
Hf
X
.3
.4
.3
.4
.3
.4
.5
.2
.2
.2
.3
.3
.2
.2
.2
.2
.2
.3
.2
.2
t
SD
.4
.5
.3
.4
.3
.4
.5
.0
.0
.0
.3
.3
.0
.0
.0
.0
•0 .
.3
.0
.0
* Mean of 8 sites (see Table 2) and 3 sampling dates (7/72, 6/73 and 9/73).
** Standard deviation.
-------
Table 32. MEAN AND STANDARD DEVIATION OF TOTAL HEAVY METALS OF SOILS FROM
MUSKEGON SPRAY AREA-BASELINE DATA ROSCOMMON SAND.
CO
Depth
PTTI
L.U1
0-15
15-30
30- /,6
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
244-259
259-274
274-290
290-305
F
X*
4200
4200
3700
3300
2600
2600
2500
2600
2600
2700
2800
2500
2300
2300
2500
2500
2800
2700
2400
2400
e
SD**
2400
2700
2000
1600
950
1200
1100
1100
1300
1400
1300
1100
990
990
940
980
1300
1300
990
990
Mr
X
71
59
51
55
54
56
54
59
58
61
56
55
49
48
41
50
53
66
52
53
i
SD
73
39
31
26
24
20
27
31
25
30
26
28
20
24
30
36
38
44
30
24
X
22
17
15
14
16
15
20
17
15
17
19
18
16
15
15
19
16
34
14
13
Zn
SD
ppra -
9.4
10
9.1
7.2
9.6
9.0
16
10
8.5
8.6
12.4
13
12
6.3
6.1
14
8.0
100
7.9
6.5
Cu
X
14
13
13
11
11
8.4
9.0
9.7
8.2
9.5
9.3
7.7
8.5
8.2
10.2
8.5
8.2
8.0
7.7
8.4
SD
13
12
15
18
18
10
10
10
9.9
12.9
11
10
10
11
12
10
9.1
10
10
11
PI
X
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
.7
b
SD
.9
.9
.9
.9 .
.9
.9
.9
.9
.9
.9
1.0
.9
.9
.9
.9
.9
.9
.9
.9
1.0
HF
X
.4
.2
.2
.2
.2
.2
.2
.3
.2
.3
.3
.2
.2
.2
.3
.3
.2
.2
.2
.2
r
SD
.5
.0
.0
.0
.0
.0
.0
.2
.0
.2
.3
.0
.0
.0
.3
.3
.0
.0
.0
.0
* Mean of 9 sites (see Table 2) and 3 sampling dates (7/72, 6/73 and 9/73).
** Standard deviation.
-------
Table 33. MEAN AND STANDARD DEVIATION OF TOTAL HEAVY METALS OF SOILS FROM
MUSKEGON SPRAY AREA-BASELINE DATA AUGRES SAND.
Fe
Mn
Zn
Cu
Pb
Hg
cm
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
244-259
259-274
274-290
290-305
X*
3000
2800
2600
2900
2400
2400
2400
2500
2400
2400
2400
2400
2400
2100
2100
2000
2600
2300
2300
2600
SD**
2800
2400
1900
1500
970
830
820
880
910
1100
990
1700
1100
690
980
910
1700
900
660
1200
X
60
53
4§
68
47
54
50
51
50
50
46
39
50
42
43
42
39
37
43
42
SD
34
25
26
33
26
24
22
17
19
15
27
24
29
25
24
22
18
16
25
15
X
25
28
19
18
20
19
23
22
18
19
21
19
17
26
17
17
19
20
19
18
SD
ppm
17
29
13
15
13
16
24
22
16
15
22
11
13
22
14
14
15
14
14
13
X
15
16
13
13
16
12
16
16
13
8.2
11
9.1
12
9.6
10
9.5
10
7.8
9.3
8.5
SD
24
' 23
25
25
25
26
27
29
20
9.1
12
12
18
13
11
13
14
10
12
11.9
X
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
.9
SD
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
11.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
X
.4
.2
.3
.4
.2
.2
.4
.4
.3
.2
.4
.3
.2
.4
.3
.2
.4
.4
.2
.3
SD
.5
.2
.2
.6
.2
.2
.3
.4
.2
.2
.4
.3
.2
.3
.2
.2
.7
.3
.2
.3
* Mean of 7 sites (see Table 2) and 3 sampling dates (7/72, 6/73 and 9/73).
** Standard deviation.
-------
Table 34. MEAN AND STANDARD DEVIATION OF TOTAL HEAVY METALS OF SOIL FROM
MUSKEGON SPRAY AREA-BASELINE DATA GRANBY SAND.
Ui
Depth
cm
0-15
15-30
30-46
46-61
61-76
76-91
91-107
107-122
122-137
137-152
152-168
168-183
183-198
198-213
213-229
229-244
224-259
259-274
274-290
290-305
F
X*
4800
4600
3500
3000
3000
2600
3100
2900
3200
2900
2700
2700
3000
3300
2900
2900
2800
2700
2700
2900
e
SD**
2100
2300
2200
1300
1200
660
1100
910
1400
1200
650
960
1200
1800
1000
1400
850
840
850
1200
b
X
95
91
86
76
59
52
60
63
75
66
55
52
58
58
52
52
52
50
47
54
In
SD
46
58
73
75
56
23
34
31
43
38
27
33
26
32
27
30
26
25
23
31
Z
X
40
37
32
25
29
21
22
23
25
22
23
24
23
24
27
27
23
27
25
22
n
SD
ppm -
29
31
26
22
31
19
19
19
26
22
21
21
22
23
25
25
20
28
25
19
Cu
X
12
15
11
8.0
8.5
5.6
5.2
6.1
5.3
6.4
7.1
8.6
6.0
8.2
7.1
9.5
8.4
9.0
6.1
6.6
SD
12
16
13
9.3
12
7.2
9.6
10.9
8.3
9.3
14
16
8.6
14
14
18
13
15
9.3
8.9
Pb
X
1.2
1.2
1.2
1.2
1.2
1.2
1.2
1.2
1.2
1.2
1.2
1.2
1.2
1.2
1.2
1.2
1.2
1.2
1.2
1.2
SD
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
1.0
HF
X
.2
.2
.2
.2
.2
.3
.3
.4
.3
.3
.2
.3
.3
.4
.4
.2
.3
.3
.3
.4
r
SD
.2
.2
.2
.2
.2
.4
.2
.5
.5
.4
.2
.5
.4
.6
.5
.2
.2
.2
.2
.5
* Mean of 8 sites (see Table 2) and 3 sampling dates (7/72, 6/73 and 9/73).
** Standard deviation.
-------
Table 35. CHANGES IN CHELATE EXTRACTABLE Fe, Mn, Zn and Cu
AFTER APPLICATION OF WASTEWATER.
cr>
Chelate
Sampling*
Extractable Period
Metal
Fe
Mn
Zn
Cu
Soil Type and Depth
Rubicon
0-15cm
Bkg
Sept. 1975
Bkg
Sept. 1975
Bkg
Sept. 1975
Bkg
Sept. 1975
72
17
10
1.5
1.7
1.2
0.3
ND
135-150cm
7
4
1.6
0.4
0.3
0.1
0.2
ND
Ros common
0-15cm
107
22
2.9
2.1
1.7
1.4
0.4
ND
135-150cm
AuGres
0- 5cm
18 77
14
1.1
0.4
0.5
0.3
0.5
ND
26
3.0
0.7
2.1
0.8
0.4
ND
135-150cm
26
11
0.9
ND
0.5
0.3
0.2
ND
Granby
0-15cm
160
20
2.8
1.5
3.1
1.8
0.5
ND
135-150cm
85
16
0.9
0.2
0.8 .
0.1
0.4
ND
* Bkg is an average of the three sampling periods prior to application of wastewater,
ND is less than .2 ppm for Mn and Cu.
-------
CHELATE EXTRACTABLE HEAVY METALS
Chelate extractable Zn, Cu and Mn have been measured in soils to es-
timate that fraction of these heavy metals that are available for plant
uptake. Thus, this measure has been used here to estimate the fraction
of heavy metals which may be susceptible to incorporation into our
food chain. It is also probable that this fraction would be more sus-
ceptible to movement in soils than would precipitated forms of the
heavy metals.
Levels of chelate extractable heavy metals were much higher in the
surface horizons than in the subsurface layers. This strong associa-
tion with soil horizons that were high in organic matter is to be ex-
pected.
The most noticeable effect of operation of the system was the reduction
in chelate extractable heavy metals, particularly Fe and Mn, by the
time of the seventh sampling in September 1975. For example, extrac-
table Fe decreased from 72 to 17 ppm for the Rubicon sand, and the
other soils were comparable. A large part of the extractable Fe was
probably associated with organic matter. When the land was drained,
placed under cultivation, and irrigated, the organic matter was mixed
by implements and generally handled in a manner which resulted in its
decomposition. This reduced the soil's ability to maintain the Fe
in a soluble or extractable form. The pH of the applied wastewater
was about 7.2 which resulted in increases in the soil pH (see Section
IV). This is expected to result in precipitation of the heavy metals,
particularly Fe and Mn, in the pH range of the soils at the Muskegon site.
There was no evidence of accumulation or movement of heavy metals
in the soils even after application of 380 cm (150 inches) of wastewater.
This would indicate that the site should operate effectively in heavy
metal removal for more than 50 years at the present rate of input.
67
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SECTION VI
SOIL PHYSICAL PROPERTIES
STUDY SITES
This section gives data and interpretation of physical properties of
the soils at the Muskegon land treatment site which may be important
to application of wastewater. A discussion of the changes in physical
properties of the soils after application of wastewater is included.
The discussions are arranged in the following order: study sites;
methods of study; resu?.ts and discussion; and addendum.
Originally nine study locations were selected. These included sites
which were thought to be characteristic of each of the four main soil
series on the project. These included AuGres, Granby, Roscommon,
and Rubicon soil series. Two sites were selected for each series.
They were selected so that they would occur in different irrigation
circles and in large areas of occurrence of the soil series. The sites
also had to be accessible for the infiltration equipment. AuGres sites
were selected on circles 23 and 40, Granby sites on circles 46 and
47, Roscommon sites were on circles 42 and 48, and Rubicon sites were
on circles 3 and 5. Initially there was a finer-textured Granby on
circle 42 which was thought to be interesting to study; however, after
the first year it was evident that this site was covered with a silt
fill, was actually not a natural soil, nor was it a major component
of the project. Therefore, the Granby with silt fill, which was studied
the first year on circle 42, was abandoned the following year. After
the first year and the initiation of the water spreading, the Roscommon
site on circle 48 was no longer accessible; therefore, a new site was
selected on circle 50.
METHODS OF STUDY
Infiltration
Infiltration measurements were made in the field, using concentric
ring infiltrometers with rings of 12.5 and 22.5 cm (5 and 9 inch)
diameter. The measurements were replicated ten times on the surface
soil and five times on the subsoil. The rings were driven 2.5 to 5
cm (1 to 2 inches) into the surface of the top soil or subsoil after
excavation for the measurement. Using large automatic burets set at
2.5 cm (1 inch) above the surface of the soil, water was measured as
it infiltrated the center 12.5 cm (5 inch) ring. The outside ring
was maintained at the same water level with a constant water level
device. Infiltration measurements were made at 5-minute intervals
for the first half hour, ten-minute intervals for the second half hour,
and at 15-minute intervals for the next four hours, for a total in-
filtration time of 5 hours. The average of the first hour is considered
the initis.1 dry infiltration rate. The average infiltration rate for
the last hour is considered the minimum dry infiltration rate. Soil
68
-------
was allowed to drain naturally from 12 to 18 hours, and then the wet
infiltration run was performed in the same manner for an additional
five hours. The initial wet is the first hour's infiltration, the
minimum wet is the fifth hour infiltration. Before the initial dry
infiltration, moisture samples were taken and are recorded with the
infiltration analyses.
Mechanical Composition
Mechanical composition was determined by the Bouyoucos Hydrometer
Method. Fifty grams of soil was dispersed by adding 100 ml of a 5%
hexametaphosphate solution and water and then stirring on a mixer dis-
persing unit for 5 minutes. The two-hour hydrometer reading was used
as the measure of clay. The dispersed sample was then washed through
a 325-mesh sieve. The total sands were dried and weighed. The dry
sands were split to one-quarter with a sample splitter and dry sieved
with standard sieves on a sieve shaker for 15 minutes.
Hydraulic Conductivity and Soil Water _Ch_ar_act_eris_t_ic_
Soil cores were collected at the site of the infiltration determina-
tion, using 7.5 cm (3 inch) diameter, 7.5 cm (3 inch) long cylinder,
and a standard hand driven core sampling apparatus. These samples
were taken of the surface 3 inches, which was entitled A , of the B
horizon, and of the underlying material which was designated as C.
These samples were taken with ten replications packed in individual
cartons and transported to the laboratory. In the laboratory, samples
were covered on the bottom with a sheet of filter paper which was held
in place by cheesecloth and a rubber band. The samples were saturated
with water for a period of several days, and then the other analyses
were performed.
Cylinders (2.5 cm (one inch) deep) were attached to the core samples,
and the saturated core sample was placed on a Buckner funnel with 1.25
cm (1/2 inch) of water applied at a constant head using a Mariott bottle
to maintain the water lavel. The amount of water which drained from
the sample for one-half hour was measured and the hydraulic conductivity
calculated.
The saturated samples were then weighed and placed on a series of blot-
ting paper tension tables adjusted to 0.01 atmosphere, 0.02, 0.03,
0.04 atmospheres of tension. Samples were allowed to equilibrate
for two days, weighed, and moved to the next tension. From there,
the samples were placed in a pressure plate apparatus and weighed after
a 2-day equilibrium at 0.1, 0.33, and 1.0 atmospheres pressure. After
this, the samples were oven dried and reweighed. From this data, the
soil water characteristics from saturation to one atmosphere were cal-
culated on a percent water-by-volume basis. Bulk density was calculated
from the oven dry weight and volume of core. Pore space was calculated
using the saturated water loss.
69
-------
Aeration and Redox
Aeration measurements were made using the platinum microelectrode
method of Lemon and Erickson, and Redox measurements were made with
the same electrode using a portable potentiometer.
RESULTS AND DISCUSSION
Mechanical Composition
The mechanical analysis of these soils indicates they are all sands.
There is some variation in the amount and distribution of the sands
between the various soil series, but there is also considerable vari-
ation between different samples taken from the same sampling area.
Only the Granby soil on circle 47 had detectable amounts of clay, and
then only 1% was present. The bulk of the sands were in the medium
and fine sand range or from 100 to 500 microns diameter.
These soils have single grain structure except for the occasional
Fe cemented ortstein horizons. With this exception, they should be
durable to tillage and other manipulations. The only physical problem
is of water retention or drouthiness.
Soil Water Characteristics, Bulk Density and Hydraulic Conductivity
These determinations were all made on the same core samples. Because
there did not appear to be any trends in these values from successive
samplings, all of the values were averaged and presented in table 36.
When the eighty values (two sites sampled four times with ten samples
per sampling) for each soil series are compared, they are remarkably
similar.
All the A horizons hold more water and have a lower bulk density
than the B or C horizons. The deeper horizons decrease in water re-
tention with depth. There is some additional water held by the im-
perfectly drained AuGres and Roscommon that had more organic matter.
The 0.1 atmosphere moisture percentage might be considered the field
capacity (water present in soil after free drainage) of these soils.
Considering this value, the A^ of the Roscommon averaged 30% as com-
pared to 19% for the Rubicon. The deeper horizons were quite variable
from sample to sample, but the averages were quite similar, ranging
from 10 to 16%, except for Rubicon C which was lower. If either of
the Granby soil sites had had a mucky surface, as some 01 the Granby
on the project does, the moisture characteristic would have been higher
and the bulk density less.
The bulk densities of these sands were similar, although these values
for the A were altered early in the season by tillage.
All of the average hydraulic conductivities were quite similar except
70
-------
Table 36. SUMMARY OF AVERAGES OF SOIL PHYSICAL PROPERTIES BY
SOIL SERIES AND HORIZONS
Soil Type
Rubicon Sand
Granby
Ros common
AuGres
Horizon
Soil Water Characteristics
Tension - atm.
0.01 0.1 0.33 1.0
Ap
B
C
A
P
B
C
A
P
B
C
A
P
B
C
-Percent
43
38
38
42
38
35
44
35
33
44
40
34
water
19
10
8
25
16
10
30
16
10
25
15
11
by
18
9
8
18
10
6
23
10
6
20
12
7
volume-
14
8
7
15
8
5
22
8
5
18
10
6
Bulk
Density
g/cc
1.4
1.6
1.6
1.4
1.6
1.6
1.2
1.6
1.7
1.2
1.5
1.6
Hydraulic
Conduc-
tivity
cm/hr
32
54
84
16
33
40
34
28
42
38
33
38
-------
for the Granby A which was about one-half the average and the Rubicon
C which was twice the other values. All these values are high and
confirm that these are very permeable soils.
Infiltration
The infiltration determinations are summarized in table 37 giving
the values at each of the four samplings. The data is extremely vari-
able, and no obvious trends are evident. Soil variability seems to
be amplified by the infiltration measurement even though each value
is an average of ten measurements for the surface and five for the
subsurface. Much of the surface had just been cleared, and the sampling
occurred as it was being brought under cultivation and irrigation.
The subsoils in these sands are also very variable. Nevertheless,
all of the values are extremely high; the lowest reading was about
10 cm per hour. There should be no problem with water application with
infiltration rates of these soils as long as there is adequate under-
drainage.
Oxygen Diffusion Rates and Redox Potential
Oxygen diffusion rates were determined after the heavy application
of wastewater that occurs at the far end of a large irrigation rig.
Even though the water suood on the surface in the lower places for
fifteen to thirty minutes, the duration of oxygen deficient conditions,
which occurred after visible infiltration from the surface ceased,
persisted for less than thirty minutes. Under these rapidly changing
conditions, plants would not be harmed by this stress. The redox po-
tentials in the soil would not be reduced either.
Under several of the circles, where the drainage system has failed,
flooding of the soil has developed. We were not aware of this as our
field crew had completed their measurements before this developed.
Under these conditions of drainage failure, oxygen deficiencies and
redox change are to be expected and plant growth may be adversely af-
fected. The solution of this problem is to bring the drainage system
up to the original specifications.
ADDENDUM
Since this study was completed, small areas of Saugatuck and areas of
slowly permeable AuGres soils have been observed in circle 26. These
soils have not been studied. They are difficult to locate until after
a period of irrigation reveals their location. Once these areas have
been found, they should be mapped and studied to determine what sort
of modification is necessary to overcome the flooding that is occurring
on these soils.
72
-------
Table 37. SUMMARY OF INFILTRATION RATES DETERMINED DURING 1973-1975.
Infiltration Rates
Condition
Time *
Soil Type
Rubicon
Surface
Granby
Surface
Subsurface
Roscommon
Surface
Subsurface
AuGres
Surface
Subsurface
Initial Dry
Circle
Number
3
5
46
47
46
47
42
48
42
48
23
40
23
40
1st
82
63
26
13
76
73
26
58
51
40
74
23
39
43
2nd
79
50
44
31
125
14
29
49
60
32
50
29
31
39
3rd
47
59
49
43
86
45
39
48
51
19
51
40
65
22
4th
90
80
48
39
64
93
29
23
26
35
46
67
53
51
1st
51
48
12
7
51
34
17
38
40
33
45
15
49
18
Initial Wet
2nd
__ /u —
68
46
30
17
60
6
27
31
50
21
53
15
39
26
3rd
36
28
23
20
35
19
15
27
28
11
25
16
44
13
4th
42
90
22
18
30
50
16
11
13
27
22
36
26
37
1st
51
48
9
2
36
29
12
25
44
26
37
18
34
21
Minimun Wet
2nd
64
42
39
15
61
4
23
29
57
17
38
15
37
31
3rd
48
53
14
15
36
57
12
8**
13
22**
18
38
30
37
4th
35
26
19
17
41
19
12
19
35
10
21
17
44
11
Time of sampling was 1st in Spring 1973, 2nd in August 1973 before the application of wastewater, 3rd
in summer 1974 after limited wastewater application and 4th in Summer 1975 after all the circles had
a full year of application.
** Circle 48 was not accessible for the 3rd and 4th sampling so Circle 50 was substituted.
-------
SECTION VII
MICROBIAL STUDIES
The principal objective of the work discussed in this section was
to determine the type and quantity of microorganisms present on the
Muskegon land treatment site, with particular reference to those in-
volved in nitrogen transformations.
Microbial populations were determined on three soils representative
of the soil diversity present at the Muskegon site. The populations
were analyzed by the following methods: nitriflers, MPN (most probable
number), using an ammonium carbonate medium and testing for the ap-
pearance of N03; denitrifiers, MPN in N03 broth incubated anaerobically
and tested for disappearance of both NO^ and NC^; aerobes, plate count
on soil extract agar; anaerobes, MPN in NOo broth and observing tur-
bidity.
The most striking result is the low numbers of nitrifiers on the Rubi-
con and AuGres soils r.t the start of irrigation (table 38). This
is likely due to the low pH, 4.6 and 6.0, respectively, since acidic
conditions are known to be unfavorable to chemolithotropic nitrifiers.
The high NH^ in the soil at the Rubicon site is also explained by
this nitrification limitation. However, as wastewater was added, the
pH increased, allowing proliferation of nitrifiers at the expense of
NH^ , their energy source. The initial low pH of the Rubicon site
was due to the forest cover. By comparison, the farmed Granby soil
had a neutral pH, high nitrifier population, and low NH^ at the onset
of irrigation. It maintained this quasi-steady-state condition through
the second year.
The denitrifier population increased slightly with irrigation, parti-
cularly in the Rubicon soil. The denitrifier population relative to
total aerobes and anaerobes was quite low in all of these soils com-
pared to most other agricultural soils. A possible explanation is
the low organic matter and aerobic conditions of these very sandy soils.
The aerobic population was fairly stable through the irrigation.
It was significantly higher in the Granby soil as expected because
of its higher organic matter content.
The anaerobic populations showed a c'ecrease with wastewater irrigation.
A possible explanation is that sporeforming anaerobes, i.e., clostri-
dia, may have been stimulated to germinate but did not survive under
the aerobic conditions present.
In summary, it is clear that the irrigation had no detrimental effect
on the soil microbial community, and, in the case of the nitrifiers,
it stimulated their development, thus assuring the conversion of
to NO^ in the soil.
74
-------
Table 38. CHANGE IN MICROBIAL POPULATIONS AND SELECTED CHEMICAL
PARAMETERS IN RESPONSE TO INITIAL WASTEWATER IRRIGATION
ON THREE SOIL TYPES.
Site
5
(Rubicon)
24
(AuGres)
46
(Granby)
Date
6-11-74
8-05-74
6-23-75
9-10-75
6-11-74
8-05-74
6-23-75
9-10-75
6-11-74
8-05-75
6-23-75
9-10-85
Microbial
Nitrifiers
(xlO1)
2.3
470
1600
4200
13
160
2800
1700
1900
420
1400
7000
populations
Denitrifiers
(xlO3)
8.4
48
46
170
22
49
42
88
46
36
320
110
(nos'g dry
Aerobes
(xlO")
3.6
4.4
1.2
15
120
4.0
5.4
8.3
18
10
9.4
12
wt"1)*
Anaerobes
(xlO5)
75
22
2.6
13
98
10
3.8
17
55
23
22
11
Samples were taken from the same site. Four replicate soil samples,
each comprised of four subsamples, were taken from the same site.
75
-------
Table 38. CHANGE IN MICROBIAL POPULATIONS AND SELECTED CHEMICAL
PARAMETERS IN RESPONSE TO INITIAL WASTEWATER IRRIGATION
ON THREE SOIL TYPES. (CONTINUED)
Water added
27.8
33.0
41.2
pH
7.3
5.7
7.0
NH^-N
N03-N Total C
0.6
2.2
0.7
7.0
58.2
10.6
2.2
4.4
2.1
Site Listing
(cumula-
tive
85.
107.
148.
71.
80.
113.
in.)
1
7
7
2
7
6
(ppm)
4.
6.
6.
6.
6.
7.
6.
6.
6
8
0
6
0
0
5
2
40.
20.
3.
0.
1.
7.
2.
0.
8
0
4
2
1
8
5
2
(ppm) (%)
2.
5.
9.
8.
6.
1.
6.
9.
3
2
6
1
7
1
7
5
2.
0.
1.
1.
1.
1.
1.
2.
0
7
0
1
9
5
7
8
Forest cleared
in 1973
Abandoned
land
farm
Actively farmed
76
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SECTION VIII
PESTICIDES AND INDUSTRIAL TRACE ORGANICS
INTRODUCTION
It is to be expected that wastewaters from a large municipality will contain
a wide spectrum of potentially toxic trace organics originating in industry,
warehouse facilities, or distribution and trade channels. Also, in a newly
established system, there is the probability that not all sources of storm
flow have been identified and isolated from the wastewater collection network.
In the Muskegon and Whitehall systems, such storm flows can originate in
areas of intensive vegetable production as well as in urban landscapes.
Until non-point sources are identified and isolated or otherwise regulated,
the sewage collection system can serve to channel pesticides in runoff and
sediments from scattered areas of use to a common point—the wastewater treat-
ment facility.
Data reported in this section represent a surveillance level monitoring of
soils and waters associated with the two Muskegon County wastewater manage-
ment systems. Four objectives were in view:
a) To obtain an inventory of readily detectable and potentially
toxic pesticides and other trace organics in incoming raw sewage.
b) To derive preliminary information regarding the fate of trace
organics at various stages of treatment.
c) To obtain a baseline inventory of trace organics in representative
soils prior to irrigation with wastewater.
d) To observe changes in level and profile distribution that might
provide an early indication of the extent to which recalcitrant
compounds in wastewater may accumulate in soils and pose a long
term residual threat to crop production and terrestrial wildlife
or to contiguous aquatic environments and groundwater supplies.
Attention was focused on organic species which can be detected at very low
concentrations by gas-liquid chromatography (GLC), using an electron capture
detector (ECD). These include many of the persistent halogenated compounds
of environmental concern.
Sampling of wastewaters was initiated with the first flow of raw sewage to
the Muskegon Wastewater Management System in June 1973. Monthly composites
77
-------
of raw sewage from June through November 1973 were used to inventory chro-
matographic peaks, make tentative peak assignments and modify procedures for
routine analysis. The first useful analyses of raw sewage were obtained in
December 1973, at which time routine monthly analysis was initiated (monthly
composites of twice-daily grab samples). Beginning in April 1974, daily grab
samples were composited for monthly analysis of discharges (after aeration
and settling) into the storage lagoons. At this time also, monthly composit-
ing (daily grab samples) was begun at Mosquito Creek and Black Creek outfalls
(SW-05 and SW-34, Fig. 1). After field irrigation began in May 1974, flows
out of storage (before and after chlorination) were composited periodically.
At Whitehall, routine monthly analysis of raw sewage and of treated dis-
charges into storage was begun in April 1975 (monthly composites of weekly
grab samples).
Eight special study sites, representing four soil types, were sampled twice
before wastewater was applied and twice yearly since full scale irrigation
was initiated in 1974. Additional analyses for background were performed
on soils from 25 sites sampled in 1972 or 1973.
The special study sites at Muskegon (Fig. 1) were on AuGres sand (sites 03
and 04, circles 21 and 24), Granby sand (sites 08 and 26, circles 47 and 44),
and Roscommon sand (sites 16 and 17, circles 41 and 42). Two sites at
Whitehall (not shown in Fig. 1) were on Rubicon sand (sites 30 and 31,
circles W-3 and W-l).
GLC peaks which correspond to those for 29 known reference chemicals have
been encountered in soils or waters. The corresponding peak positions in
output from two different GLC columns were monitored routinely for all ex-
tracts of soils and waters. Thin layer chromatography and, for certain
chemicals, a third or fourth GLC column were also used for confirmation.
Three additional peaks were monitored routinely, beginning August 1975, but
have not been identified with known compounds. These were frequently prom-
inent in raw influent and in discharges to storage. They appeared at greatly
attenuated levels in soils and in outfall waters.
PROCEDURES
Sampling methods and analytical procedures are described in detail in
Appendix II. They are described briefly below.
Sampling and Extraction of Soils
Four cores were composited from depths of 0 - 15, 46 - 61, and 91 - 107 cm
(0 - 6", 18 - 24", and 36 - 42")—the third depth was not sampled prior to
1975. Aliquots (100 g field moist soil) were deactivated with water and ex-
tracted with two successive 100 ml aliquots and a third 50 ml aliquot of 2:1
benzene-isopropanol. The isopropanol was removed with water. The benzene
extract was dried by passing through anhydrous sodium sulfate and concen-
trated twice to a final volume of 10 ml.
78
-------
Sampling and Extraction of Waters
Water samples were taken daily (or as noted in tables) and accumulated at
4° C over periods of 2 to 5 weeks. Raw influent and discharges into storage
through 1975 were separated by centrifugation and filtering into aqueous and
particulate phases. Particulate phases were extracted with 2:1 benzene-
isopropanol as for soils. Water samples (1.5 liters) were extracted with
4 successive 50-ml aliquots of methylene chloride. The extract was concen-
trated to 5 ml and transferred into benzene (with successive concentration
steps to remove methylene chloride). The final volume in benzene was 10 ml.
Cleanup of Extracts
Prior to analysis, benzene extracts were cleaned up and separated into
groups of chemicals by fractional elution off from Florisil.
Detection and Quantitation of Organics
Detection and quantitation were by gas-liquid chromacography (GLC), using
1.5% OV-17/1.95% QF-1 on Gas Chrom Q in glass columns (3 mm I.D. x 1.83 m).
Identification was by retention time confirmed on one or more additional
columns and by thin layer craromatography (silica gel). A Beckman GC-5 was
used, with a non-radioactive electron capture detector (helium arc discharge).
Instrument parameters were optimized daily for maximum sensitivity. Integra-
tor (Autolab System I) parameters were set to reject peaks with heights less
than 3 times baseline noise.
An injection volume of 4 yl was used for samples. Reference standards were
injected after every third sample, at volumes ranging from 1 to 6 pi to
provide a standard curve. Standard concentrations of 1/10 X, 1 X, or 10 X
were used to provide ranges of linear response appropriate for sample con-
centrations encountered.
Confirmation of Peak Identities
Chemicals as reported have been confirmed routinely on two columns
(1.5" OV-17/1.95% QF-1 and 6% QF-1), and by thin layer chromatography
(silica gel). For certain chemicals and extracts, 2% SE-30 or 3% DECS
columns have also been used for confirmation. (Table II-2, Appendix II).
TRACE ORGANICS IN WATERS
With the exception of diethylhexylphthalate (DEHP), chemicals reported for
incoming wastewaters in this study are pesticides or isomers or metabolites
of pesticides. Identification of sources was beyond the scope of the in-
vestigation. However, some consideration of probable sources and modes of
entry for trace organics into wastewater flows at Muskegon and Whitehall
will be helpful in evaluating the data.
79
-------
Probable Sources and Modes of Entry
Sewage treated at Muskegon and Whitehall comes from 14 municipalities, with
approximately 140,000 residents and 200 industries. Most of it (27 MGD in
1975) goes into the Muskegon system. Flows at Whitehall are about 1 MGD
(Muskegon County Dept. of Public Works, 1975; USEPA, Region V, 1976).
Sixty percent of the flows at Muskegon come from industry, with the major
contributor a paper manufacturer. A major contributor at Whitehall is a
tannery. Manufacturers of chemicals include several companies that produce
primary chemicals and intermediates, pesticides, plastics, resins, elasto-
mers. Other industries that undoubtedly use organic chemicals of environ-
mental concern are manufacturers of foundry products, heavy machinery,
automotive engines, parts and accessories (Directory of Michigan Manufac-
turers, 1976).
Supporting these basic industries are warehousers and distributors serving
local, state, national and international trade channels by rail and truck,
as well as through the Port of Muskegon and the St. Lawrence Seaway. There
are also numerous operators involved in various aspects of industrial waste
disposal: waste haulers, waste takers and processors, barrel Tenderers, etc.
This complex of activities affords numerous opportunities for point source
contamination due to accidents, inappropriate handling or storage, or in-
adequately controlled disposal or discharge.
"Truth in pollution" legislation (Act 200, Mich. P.A. 1970, and later amend-
ments to Act 245, P.A. 1929) requires that industrial and commercial pro-
ducers of wastewaters (other than sanitary sewage) file annual reports with
the Michigan Water Resources Commission, listing critical materials and waste-
water outfalls. A fee is assessed to cover costs of surveillance by the
Commission.
Types of outfall registered by industries in the Muskegon and Whitehall areas
include discharges into surface waters (directly or through storm sewers) and
a variety of discharge methods that may lead ultimately to groundwater (la-
goons or seepage ponds with no outlet, septic tanks and tile fields, overland
flow). Large quantities of noxious liquid wastes and recoverable by-products
are transported by licensed waste haulers to independent industrial waste
processors operating locally, elsewhere in Michigan, or out of state. Sludges
that accumulate in lagoons and seepage ponds have in the past leen inciner-
ated y buried in landfills, or abandoned in favor of new discharge sites.
Since the two county treatment systems became operational, state and local
authorities have encouraged the diversion of compatible wastewaters from
industry into sanitary sewers connected to the county systems. The major
contributor to flows at the Muskegon site (the paper mill) initiated diver-
sion in June 1973. The tannery at Whitehall connected up in late 1974.
The number of connected discharges has increased over the period of this
study. Diversions of 50 to 80% or more were registered by a number of
companies in 1975. However, numerous industries and a number of smaller
municipalities were either not connected or had diverted less than 50% of
80
-------
their wastewater into either system through 1975 (Michigan Water Resources
Commission, Surveillance Fee Listings, 1973, 1974, 1975).
Increasing numbers and diversity of source discharges may have contributed
to changes in spectrum of trace organics encountered in this study. It is
likely that wastewaters will become increasingly complex and variable in
composition as more of the existing discharges from industry and from sub-
urban residential and commercial areas are connected to the system and as
new industries, attracted by the county's wastewater treatment capabilities,
move into the area.
A wide range of chemicals is used or produced in large volume. The bulk of
these are identified in critical materials registrations only by broad cate-
gories (chlorinated benzenes, nitrobenzenes, aromatic amines, etc.). The
probable range of organic species which may appear in wastewaters is aug-
mented by unknown or unlisted by-products of manufacturing or of pretreat-
ment before discharge. Discharges can vary widely from time to time with
production schedules chat may involve a succession of weekly campaigns for
production of two or more intermediates leading to a major product. Waste-
waters from paper manufacturing are extremely complex and vary with pulping
method, pulp species, and with treatment given to palping effluents before
discharge (Hrutfiord et al., 1975).
Numerous instances of contamination of surface and groundwaters associated
with chemical industries in the Muskegon and Whitehall areas have occurred
(Muskegon Chronicle, December 12, 1975; Detroit Free Press, December 29, 1976
and April 12, 1977). The Michigan Water Resources Commission has determined
that contaminated groundwaters shall be purged by pumping into the county
wastewater treatment systems. It is unlikely that much of this was done
during the period of this study, however.
At the present state of the art, both dischargers and control agencies are
handicapped by uncertainties regarding parameters which should be monitored
and by analytical difficulties in resolving complex mixtures and positively
identifying individual organic species.
The lack of positive identification by other than chromatographic parameters
seriously limits the credibility of chemical assignments given in this report.
Phthalates are listed as critical materials by a number of companies, sup-
porting the identification here of DEHP. Of the pesticides, only phorate
(ThimetR) is known to have been produced in the Muskegon area where it was
identified frequently in wastewaters in 1975. However, it appears that major
production may not have been undertaken until early 1976.
Circumstantial support for several pesticides is to be found in known pat-
terns of use and in known sales for "restricted use" pesticides which must
be reported by licensed dealars (Michigan Department of Agriculture, Regula-
tion No. 633, 1972). There is good reeson to expect that pesticides in
current use or persistent residues frot. past use will enter wastewater flows,
directly or indirectly, from hydrologic systems that converge in the
Muskegon and Whitehall areas.
81
-------
Major industrial dischargers in the Muskegon area take their feedwaters from
Muskegon Lake, Mona Lake or streams that flow into them, or from contiguous
groundwaters. Sixty percent of the annual wastewater flow at the Muskegon
treatment site comes from the paper mill, which takes essentially all of its
processing water from Muskegon Lake. Contaminants in Muskegon Lake may well
appear at the treatment site at levels reduced by less than fifty percent.
Much greater dilution would be expected for contaminants from Mona Lake or
other lesser sources of feedwater.
Pesticides and other pollutants in these lakes can originate locally in
storm flows from residential, commercial and industrial areas. Chronic con-
tamination of surface and groundwaters by discharges from chemical industries
has occurred along streams entering both lakes. Both receive drainage from
watersheds extending northeasterly, hence normally downwind. Thus, airborne
pollutants generated locally can be intercepted and returned. Vegetables,
mainly celery, are grown in drained lowlands just east of both lakes. Flood-
waters of the Muskegon River occasionally wash across the diked fields near
its mouth.
Water and sediments entering Muskegon and Mona Lakes can also carry contam-
inants from point and non-point sources scattered widely over extensive river
basin areas. The Muskegon River basin is one of the largest in Michigan
(2660 nn/, or 6890 knr). Fifty percent of the area is forested and includes
a large proportion in recreational areas and concentrated resort development;
25% is in agriculture, including important areas of cash crop and intensive
vegetable production. Over 20 industries and 9 municipalities use the sur-
face waters of the river for wastewater assimilation (Great Lakes Basin Com-
mission, 1976; Wright, 1974; see also National Cooperative Soil Surveys for
Counties of Muskegon, Newaygo, Mecosta and Osceola).
The Black Creek watershed lies almost entirely in lluskegon County. There
are areas of agricultural production in the eastern half of the basin in-
cluding vegetables and cash crops on organic soils just east of the waste-
water irrigation site. A large chemical plant is located in a thinly popu-
lated marginal area along the middle reaches of the stream. The lower half
of the basin becomes increasingly urbanized on approach to Mona Lake, but
there are scattered farms, including areas near the lake, that are managed
intensively for celery and other vegetables.
A number of pesticides implicated in this study were currently and widely
used for insect control in agriculture and forestry and for landscaping and
other uses in urban, suburban, resort and recreational areas. These, and
persistent chemicals like DDT and endrin that were used extensively prior
to the 1970's, can appear in substantial concentrations in streams during
periods of heightened or turbulent flow resulting from runoff and erosion
(Miles, 1976; Snow, 1977; Truhlar and Reed, 1976).
Soluble materials and pesticide-enriched fine sediments carried by streams
can be widely dispersed in receiving lakes. Heavier bottom wash sediments
are also enriched with pesticide residues. Deposition of sediments in flood-
ing lowlands a^d in quiescent waters near the mouths of streams is a concen-
trating mechanism. The presence of such deposits increases the probability
82
-------
that persistent chemicals will be found in associated surface waters
(Glooschenko, 1976). Flooding lowlands are often important groundwater
recharge areas. Deposition of enriched sediments in these areas also in-
creases the potential for contamination of groundwaters (Garrett et al.,
1976).
Thus, there is good reason to expect that pesticides and other contaminants
from basin-wide sources will appear in feedwaters used by industry. At times
the concentrations may be substantial, and little change will occur between
points of intake and discharge where water is used for cooling or for large
volume processes compatible with low-grade water. This would be the primary
mode of entry into flows received at the treatment site. System failures
can occur, as when a malfunctioning sluice gate allowed high waters in
Muskegon Lake to flow directly into municipal sewerage for periods during
this study. Flows measured in the system indicate that infiltration of sew-
ers occurs also in low-lying areas during periods when the watertable is high
and that there are places in the system where storm sewers and sanitary sew-
ers are still interconnected. Unusual flows associated with storm events
or high water are, however, small when compared to base flow or to industrial
flows that are known to originate in feedwaters taken from lakes or streams.
Some of the circumstances described above for the Muskegon system undoubtedly
exist also at Whitehall. Celery is grown in lowlands near the mouth of White
River and along its lower tributaries in Muskegon County. The basin includes
important areas of vegetable production and general farming in Oceana and
Newaygo Counties (Wright, 1974; also see National Cooperative Soil Surveys
for these counties). Some of the fruit areas in Oceana County drain to White
River. There are scattered resort developments and recreational areas in
the basin and several small communities along the river.
The White River discharges into White Lake which opens on Lake Michigan.
White Lake also receives discharges and storm flows from a concentration of
industry around the lake as well as runoff from residential, commercial and
resort areas. Well over 90% of the wastewater volume registered in 1975 for
industrial outfalls in the Whitehall-Montague area was surface discharged
and came mainly from a basic producer of chlorinated hydrocarbons. The plant
is not connected to the Whitehall wastewater system; however, chemicals dis-
charged to the lake or airborne and intercepted on downwind landscapes might
well appear in feedwaters of other industries which do discharge into the
Whitehall system.
To monitor the full range of chemicals known or suspected of being input at
either the Muskegon or Whitehall treatment sites is beyond available funding
and probably beyond presently available methodology. Analytical difficulties
are complicated further by the likelihood that individual source chemicals
are variously altered in diverse environments along pathways of local and
regional circulation before coming together at the treatment sites. Fluc-
tuations in volume and composition of flows from individual point or non-
point sources make sampling to estimate loadings at a confluence point dif-
ficult if not impossible (Lake Michigan Interstate Pesticides Committee,
1972).
83
-------
Only electron capturing species were monitored in this study. Electron cap-
ture was used for detection and quantitation because of its sensitivity for
a number of chlorinated hydrocarbons that are known to be widely distributed
and most likely encountered. DDT, dieldrin and PCB's are of particular con-
cern in the Great Lakes Basin because of their known impact on fish and
waterfowl and their persistence in soils and sediments (International Joint
Commission, 1976; Schacht, 1972). These and other refractory organics can
be useful for tracing pathways of circulation through the environment (Arthur
et al., 1977; Miles, 1976; Roan, 1975; Snow, 1977). Abroad spectrum of
organics which might be expected from industry would not have been detected
(Garrett et al., 1976).
Chemicals reported here were identified by chromatographic methods and con-
firmed on three or more media. Nevertheless, identities are presumptive
rather than specific. The chromatographic parameters (Appendix II) are re-
producible. The methods used and the data themselves are compatible with
a large volume of data accessible in STOR.ET (Merkle and Bovey, 1974) and with
historical documentation categorized by geographical location, water types,
sources, etc. in such compilations of available data as DAM (Hall et al.,
1976) and Water DROP (Shackleford and Keith, 1976).
Raw Influent and Discharges in^o Storage
Because of the large number of probable sources and fluctuating flows from
each, the composition of incoming wastewater can vary greatly over short
periods of time. Chemicals entering sporadically may not be detected in
grab samples taken at a given station. Some GLC peaks which were not found
in raw influent did appear during the same compositing period in discharges
into storage lagoons. Peaks for most chemicals did not decline in frequency
or indicated range of concentration during aeration and settling. For these
reasons, data for raw influent and for discharges into storage are best con-
sidered together for purposes of characterizing incoming wastewaters. Data
for monthly composites are given in Tables 39 to 43. Frequencies and
ranges of occurrence are summarized for 1974 and 1975 in Tables 47 and 48.
Industrial organics —
Diethylhexylphthalate (DEHP) was the only industrial organic identified in
this study. Phthalates, as a class, have appeared on lists of critical
materials from local industries. DEHP was found frequently at Muskegon at
concentrations of 10^ to 10^ ng/1 (Tables 39 to 42). An important source
would have been from manufacture of paper products. It appeared at Whitehall
in late 1974 at about the time the leather company reported its hook-up to
the system (Table 43).
Numerous unknown peaks were not monitored. Beginning in August 1975, three
unknown peaks that were frequently observed and often prominent were inte-
grated, and their percentage contribution to total integrated peak area was
recorded. These were at 115-118 sec, 164-168 sec and 247 to 253 sec on
1.5% OV-17/1.95% QF-1 (Rt ratios relative to aldrin = 0.9, 1.27 and 1.92).
The first two peaks were not close co any major peak for any of the common
Arochlors examined (1242, 1248, 1254, 1260). The third corresponded closely
84
-------
Table 39. TRACE ORGANICS IN RAW INFLUENT, MUSKEGON, DECEMBER 1973 TO DECEMBER 1974.$
00
Ol
Month
Dec
Dec- Jan
Feb
Mar
Mar
Apr
May
May
Jun- Jul
Jul
Aug
Sep
Oct
Nov
Dec- Jan
Detected
Compositing Period
(twice daily
grab samples)
12-1-73 to 12-21-73
l?-22-73 to 1-21-74
2-1 to 2-27-74
2-28 to 3-19-74
3-20 to 4-4-74
4-8 to 4-30-74
5-1 to 5-14-74
5-15 to 5-31-74
6-1 to 7-11-74
7-12 to 7-31-74
7-31 to 8-29-74
8-30 to 9-30-74
10-1 to 10-29-74
10-30 to 12-1-74
12-2-74 to 1-10-74
means (ng/l)
'"r
i
nd*
nd
nd
nd
nd
324
35
nd
nd
nd
nd
nd
nd
nd
nd
180
I
1
fi-
nd
nd
nd
nd
nd
nd
lot
nd
nd
nd
nd
nd
nd
nd
nd
10
a:
CD
*o
rt
1
O
nd
nd
nd
nd
nd
123
363
464
nd
22
nd
nd
nd
nd
nd
243
1
n it
•o fa
o n
X cr
E o*
it 1
nd
nd
nd
nd
nd
106
2 t
nd
nd
7
nd
nd
nd
3t
nd
30
M
o"cL
an
0
!H
nd
nd
nd
nd
nd
225
nd
270
nd
lot
nd
nd
nd
nd
nd
168
p
i
W
o
nd
nd
nd
nd
nd
nd
193
nd
nd
340
nd
nd
nd
nd
nd
266
H*
g.
i
- ng/l -
89
140
nd
nd
nd
nd
323
57
79
97
268
100
6
nd
5t
116
N
§
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
404
nd
nd
404
n
»
rt
III
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
6.3xl03
6.3xl03
Is)
f
O
§
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
l.JxlO3
nd
nd
nd
nd
1.2xl03
•<
O OQ
n n
nd
nd
nd
nd
nd
323
nd
nd
nd
nd
nd
nd
nd
nd
nd
323
Q
75xl03
109x10 ~
63x10
20xl03
91xl03
358x10 3
650xl03
172xl03
21xl03
36xl03
nd
nd
199xl03
175xl03
nd
164x10 3
*nd - not detected
tBelow usual range of confident quantitation (Appendix II, Table 2).
*GLC peaks for all chemicals listed in Table 2, Appendix II, were monitored. Only chemicals detected and confirmed
on two or more GC
-------
Table 40. TRACE ORGANICS IN RAW INFLUENT, MUSKEGON, JAN TO DEC 1975.1
oo
Monti
Jan
Feb
Mar
Apr
May
Jun
Jul
Aug
Sep
Oct
Nov
Dec
Detected
Compositing
period
(twice daily
grab samples)
1-6 to 1-31-75
2-4 to 2-28-75
3-4 to 3-31-75
4-1 to 4-30-75
5-2 to 6-2-75
6-2 to 7-2-75
7-2 to 7-30-75
8-2 to 9-2-75
9-2 to 10-2-75
10-2 to 11-4-75
11-4 to 11-28-75
12-2-75 to 1-2-76
means (ng/1)
It
$
nd*
4t
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
4
a
H1
(X
H-
a
nd
nd
nd
nd
nd
nd
nd
tr**t
nd
nd
nd
nd
tr
fo
fa
I
s
28
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
28
ff
•0
rt
cr
o
hi
nd
nd
nd
nd
nd
nd
8
nd
nd
nd
90
nd
49
8?
•a
•a ID
86-
O. 0
rt n
nd
194
nd
nd
nd
nd
nd
nd
nd
nd
21
nd
108
f
OS
o
nd
nd
nd
nd
nd
34
nd
nd
nd
517
96
nd
216
P
8.
g
31
374
nd
nd
102
20
30
611
20
815
575
83
266
a
N
g-
g
nd
nd
nd
nd
nd
nd
nd
3.5xl03
nd
nd
nd
nd 3.
l.SxlO3 1
o
r
rt
cr
o
i?
347
nd
nd
nd
nd
nd
nd
nd
nd
nd
833
2x103
fT
O
rt
ft
IB
- - ng/1
rid
3.5xl03
nd
nd
2.X103
32.xlOJ
nd
9,xlQ3
6.6x103 9
7. 5x10 3
88.X103
nd
' 21.X1Q3
r
CD
O
nd
nd
nd
nd
nd
nd
nd 4
200 1
. 3x10 3
nd
nd
200 5.
3. 2x10 3
NJ
V
O
5
nd
nd
nd
nd
nd
nd
.xlO3
nd
nd
nd
SxlO3
3.5x10
V
a
W
M
M
nd
nd
nd
630
nd
nd
nd
nd
nd
nd
nd
nd
3 630
V
o
DJ
s
H
nd
nd
nd
nd
nd
nd
nd
nd
200
nd
nd
nd
200
**
a
M
•U
RJ
*^>
nd
nd
l.lxlO3
nd
nd
nd
nd
nd
nd
nd
nd
500
800
D
t§
2,6Mxl03
nd
nd
nd
677xl03
5 3x10 J
60x10 3
55xl03
nd
1,067x103
SOxlO3
193xl03
597x103
*nd - not detected
**tr = Trace
tflelow usual range of continent quantitation (Appendix II, Table 2).
+GLC peaks for all chemicals listed in Table 2, Appendix II, were monitored. Only chemicals detected and confirmed on two or more
GC columns are reported. Confirmation by thin layer was required, also, except at concentrations too low for spots to be
visualized.
-------
Table 41. TRACE ORGANICS IN DISCHARGES INTO STORAGE LAGOONS, MUSKEGON, APRIL TO DEC. 1974.-)
co
Month
April
May
May
Jun-Jul
Jul
Aug
Sep
Oct
Nov.
Dec-Jan
Detected i
Compositing
period
(dally grab
samples)
4-8 to 4-30-74
5-1 to 5-14-74
5-15 to 5-31-74
6-1 to 7-11-74
7-12 to 7-31-74
7-31 to 8-29-74
8- 30 to 9-30-74
No sample
No sample
12-2-74 to 1-10-75
Deans (ng/1)
Dieldrin
nd*
nd
nd
nd
nd
16
nd
__
—
nd
16
F°
I
O
s
244
345
nd
nd
nd
nd
nd
nd
294
leptachlor
nd
199
nd
nd
37
nd
nd
nd
118
Heptahior
epoxlde
nd
nd
nd
nd
80
nd
nd
—
nd
80
L-hydroxy-
chlordene
341
nd
144
187
512
nd
25
— .—
255
244
p
k
n
nd
nd
18
51
40
nd
nd
—
nd
36
Llndane
- ng/1 - -
224
155
92
73
151
nd
nd
151
141
I
nd
nd
nd
nd
nd
nd
127
nd
127
parathion
nd
nd
nd
nd
nd
nd
38t
__
—
nd
38
Lasso
J.4-h..1
nd
nd
nd
nd
nd
nd
12.8x103
nd
12.8xl03
Vegadex
nd
nd
nd
nd
10
nd
nd
—
nd
10
o
419xl03
348x10^
269x10^
67xl03
60xl03
nd
1,233x103
.
—
nd
216xl03
*nd • not detected
tBelow usual range of confident qualification (Appendix II, Table 2).
+GLC peaks for all chemicals listed in Table 2, Appendix II, were monitored. Only chemicals detected and confirmed on two
or more GC columns aire reported. Confirmation by thin layer was required, also, except at concentrations too low for spots
to be visualized.
-------
Table 42. TRACE ORGANICS IN DISCHARGES INTO STORAGE LAGOONS, MUSKEGON, JAN. TO DEC. 1975.
00
00
MoTif-h
Jan
Feb
Mar
Apr
May
Jun
Jul
Aug
Sep
Oct
Nov
Dec
Detected
Compositing
period
(daily grab
sauries)
1-6 to 1-31-75
2-4 to 2-28-75
3-4 to 3-31-75
4-1 to 4-30-75
5-2 to 6-2-75
6-2 to 7-2-75
7-2 to 7-30-75
8-2 to 9-2-75
9-2 to 10-2-75
10-2 to 11-4-75
11-4 to 11-28-75
12-2-75 to 1-2-76
means (ng/1)
Aldrln
nd
nd
26
nd
nd
nd
ml
nd
nd
nd
hd
nd
26
Endrin
35
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
35
lo
I
o
nd
nd
nd
nd
nd
nd
ud
tr**t
nd
nd
nd
nd
tr
1°
S
w
nd
nd
3t
11
nd
nd
nd
nd
nd
nd
nd
nd
7
i
nd
nd
nd
nd
nd
nd
nd
nd
18
nd
nd
nd
18
Heptachlor
nd
nd
nd
nd
nd
nd
nd
nd
nd
955
nd
7
481
Heptachler
epoxide
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
18
18
l-tiydroxy-
chlordene
nd
nd
nd
nd
nd
nd
nd
nd
7t
nd
2t
2t
4
B
1
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
98
p.
56
111
9
nd
tr
3t
nd
84
58
729
463
168
168
Diazinon
- ng/i - - -
3. 8x10 3
nd
nd
910
nd
nd
561
nd
nd
nd
nd
nd 1.
1.6xl03
Dlmethoate
290
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
,7xl03
995
Fhorate
nd
nd
nd
nd
nd
nd
nd
3. 3x10 3
nd
nd
31.X103
2.4xl03
12.xlO<
t*
0
nd
nd
nd
nd
260
nd
2.xl03
1.4xl03
lot
nd
1.3xl03
nd
994
2,4-D(IPE)
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
1.6xl03
nd
1.6xl03
0
332. 103
289xlOJ
nd
106xl03
nd
nd
nd
183xl03
167xl03
350xl03
2,017xHT
142xl03
448. xlO3
*nd ™ not detected
i*tr _ Trace
'''Below usual range of confident quantitation (Appendix II, Table 2).
tGLC peaks for all chemicals listed in Table 2, Appendix II, «ere monitored. Only chemicals detected ar.d confirmed on two or
more GC columns are reported. Confirmation by thin layer was required, also, except at concentrations too low for spots to
be visualized.
-------
Table 43. TRACE ORGANICS IN RAW INFLUENT AND IN DISCHARGE INTO STORAGE, WHITEHALL, APR. TO DEC. 1975. j
00
Month
Compositing
Period
(Random grab
samples)
>
3.
0
1-
1
§
o
ff
S*
ai
a. M
It 0
*
V
&«
82
s-s
§ '
R
1
3
o
C
P
8-
g
RAW INFLUENT
Apr
May
Jun
Jul
Aug
Sep
Oct
Nov
Dec
DISCHARGE
Apr
May
Jun
Jul
Aug
Sep
Oct
Nov
Dec
4-1 to 4-30-75
5-2 to 6-2-75
6-2 to 7-2-75
7-2 to 7-30-75
No sample
9-2 to 10-2-75
No sample
11-4 to 11-28-75
No sample
INTO STORAGE
4-1 to 4-30-75
5-2 to 6-2-75
6-2 to 7-2-75
7-2 to 7-30-75
No sample
9-2 to 10-2-75
No sample
11-4 to 11-28-75
No sample
nd*
nd
nd
nd
8
nd
—
nd
nd
10
nd
nd
nd
nd
nd
nd
nd
nd
nd
404
nd
nd
nd
nd
.
nd
9
nd
nd
nd
nd
nd
26
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
3t
nd
nd
nd
„.
nd
nd
nd
nd
nd
nd
nd
404
nd
nd
nd
nd
nd
nd
22
51
14
97
113
nd
3t
47
25
137
nd
0
3-
Q
ft
n
770
nd
nd
nd
nd
nd
2.5xl03
nd
nd
nd
nd
nd
F
M
o
nd
nd
nd
nd
nd
nd
nd
312
nd
nd
nd
nd
Kl
V
O
§
nd
lid
nd
nd
nd
300
nd
nd
nd
nd
nd
.
4.2xl03
M
V
a
w
w
M
M
nd
nd
9t
nd
nd
nd
—
nd
nd
nd
ltd
nd
nd
M
V
a
/-*
M
•a
•2
S.xlO3
nd
nd
962
nd
500
1.4xl03
nd
nd
nd
210
6.X103
a
n
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
2.xlo3t
5.xl03t
B ns
n «
ptachlo
tabollt
2"
9
nd
nd
nd
nd
nd
26
3t
nd
nd
nd
nd
M. P
a> -a ft
1*1
nd
22
51
14
97
113
—
404
It
nd
25
137
nd
*nd - not detected
tflelow usual range of confident quantitation (Appendix II, Table 2).
*GLC peaks for all chemicals listed in Table 2, Appendix II, were monitored. Only chemicals detected and confirmed on two or more
GC columns are reported. Confirmation by thin layer was required, also, except at concentrations too low for spots
to be visualized.
-------
Table 44. TRACE ORGANICS IN PRE-CHLORINATION FLOWS AND IRRIGATION WATER, MUSKEGON, JUNE 1974 TO DEC. 1974.
VO
O
Month
Compositing
period
(Random
grab samples)
Frechlorination flows (out of storage
Jun-Jul
Jul
Aug
Oct
Nov
Dec
Irrigation
Jul #1
#2
Aug #1
#2
Sep #1
Oct
Nov #1
n
Dec
6-1 to 7-11-74
7-12 to 7-31-74
7-31 to 8-29-74
10-1 to 10-29-74
10-30 to 12-1-74
No sample
waters (pumps fl and #2)
7-12 to 7-31-74
7-12 to 7-31-74
8-12 to 8-31-74
8-12 to 8-31-74
9-12 to 9-31-74
No sample
No sample
Detected means (ng/1)
Dleldrin
lagoons)
nd*
nd
nd
nd
nd
nd
nd
nd
nd
146
— —
nd
nd
146
ha.
i
g
in
3t
3t
nd
nd
nd
nd
nd
nd
nd
nd
- ...
nd
nd
3
1-hydroxy-
chlordene
57
nd
nd
62
nd
nd
nd
nd
nd
nd
__
nd
nd
60
P
8
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
43
143
69
P
nd
nd
nd
nd
133
- —
nd
nd
nd
nd
nd
-_.
nd
nd
133
Lindane
.
36
nd
95
32
nd
— —
371
nd
nd
nd
nd
—
41
42
93
o
315
nd
nd
nd
nd
nd
nd
nd
nd
nd
—
nd
rd
315
1
19xl03
nd
nd
nd
nd
112xl03
5 3x10 3
nd
nd
32xl03
nd
nd
_
54xl03
S
ui rt
•g&
Ho
a a
in H
3
3
nd
nd
nd
nd
nd
nd
nd
nd
—
nd
nd
3
*nd ~ not detected
t Below usual range of confident quarvtitation (Appendix II, Table 2).
tGLC ; eaks for all chemicals listed in Table 2, Appendix II, were monitored. Only chemicals detected and confirmed
on two or more GC columns are reported. Confirmation by thin layer was required, also, except at concentrations too low
for spots to be visualized.
-------
Table 45. TRACE ORGANICS IN NORTH OUTFALL WATERS (SW-05, MOSQUITO CREEK), MUSKEGON; APR 74 TO DEC 75.
VO
Month
Apr
May
May
Jun-Jul
Jul
Aug
Sep
Oct
Nov.
Dec-Jan
Jen
Feb
Mar
Apr
May
Jun
Jul
Aug
Sep
Oct
Nov
Dec
Detected
Compositing
period
(daily grab
samples)
4-8 to 4-30-74
5-1 to 5-14-74
5-15 to 5-31-74
6-1 to 7-11-74
7-12 to 7-31-74
7-31 to 8-29-74
8-30 to 9-30-74
10-1 to 10-29-74
10-30 to 12-1-74
12-2-74 to 1-6-75
1-6 to 1-31-75
2-4 to 2-28-75
3-4 to 3-31-75
4-1 to 4-30-75
5-2 to 6-2-75
6-2 to 7-2-75
7-2 to 7-30-75
8-2 to 9-3-75
9-2 to 10-2-75
10-2 to 11-4-75
11-4 to 11-28-75
12-2-75 to 1-2-76
means (ng/1)
Aldrin
nd*
nd
nd
14
nd
nd
nd
. nd
nd
nd
nd
ud
nd
nd
4t
nd
nd
nd
nd
nd
nd
nd
9
a
H.
H*
o
nd
nd
nd
nd
31
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
31
h>
i
o
s
7t
8t
8t
6t
6t
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
7
Heptachlor
nd
nd
nd
5t
47
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
5t
nd
nd
19
Heptachlor
epoxide
nd
nd
nd
ncl
25
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
It
nd
13
1-hydroxy
chlordene
nd
nd
nd
nd
145
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
145
e
S
O
nd
nd
25
nd
53
nd
nd
nd
112
lit
nd
4t
19
nd
nd
nd
nd
lh
nd
nd
nd
nd
37
T
£
o
nd
nd
nd
nd
nd
nd
nd
46
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
46
(0
nd
nd
nd
11
37
nd
nd
84
375
nd
5t
2t
178
150
nd
nd
nd
It
nd
2t
nd
nd
84
Diazlnon
nd
nd
nd
nd
nd
nd
48t
521
483
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
334
Atrazine
nd
nd
nd
nd
nd
nd -
292xlOJ
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
292xl03
1
o
298
119t
183
415
625
nd
nd
loot
nd
350
nd
nd
nd
nd
359
33t
Ifft
nd
nd
nd
nd
25t
226
2,4-D(BE)Il
nd
nd
nd
nd
203
nd
nd
nd
nd
nd
nd
nd
nd
650
195
nd
nd
nd
nd
nd
nd
nd
349
Vegadex
nd
nd
nd
32
136
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
84
I
nd
r.d
15x10
lOxlO3
3xl03t
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
115xl03
nd
nd
10xlOJ
31.xl03
*nd - not detected
tBelow usual range of confident quantitation (Appendix II, Table 2).
+GLC peaks for all chemicals listed in Table 2, Appendix II, were monitored. Only chemicals detected and confirmed on two
or :uore GC columns are reported, Confirmation by thin layer was requirfd, also, except at concentrations too low for spots to
be visualized.
-------
Table 46. TRACE ORGANECS IN SOUTH OUTFALL WATERS (SW-34, BLACK CREEK), MUSKEGON, APR 74 TO DEC 75. t
Month
Apr
May
May
Jun-Jul
Jul
Aug
Sap
Oct
Nov
Dec- Jan
Jan
Feb
Mar
Apr
May
Jun
Jul
Aug
Sep
Oct
Nov
Dec
Detected
Compositing
period
(dally grab
samples)
4-8 to 4-30-74
5-1 to 5-14-74
5-15 to 5-31-74
6-1 to 7-11-74
7-12 to 7-31-74
'/• il to 8-29-74
8-30 to 9-30-74
10-1 to 10-29-74
10-30 to 12-1-74
12-2-74 to 1-6-75
1-6 to 1-31-75
2-4 to 2-28-75
3-4 to 3-31-75
4-1 to 4-30-75
5-2 to 6-2-75
6-2 to 7-2-75
7-2 to 7-30-75
8-2 to 9-2-75
9-2 to 10-2-75
10-2 to 11-4-75
11-4 to 11-28-75
17-2-75 to 1-2-76
means (ng/1)
>
M
a.
*i
H>
a
nd*
nd
nd
22
39
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
30
h»
h>_
i
o
O
to
nd
nd
5t
2t
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
4
X
(0
•0
rt
I
M
o
n
nd
nd
It
9
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
5
«
IB
It V
•O rt
O f»
M n
H- =r
a. M
n o
H
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
6
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
6
0
i
1
nd
nd
nd
nd
nd
nd
16
nd
nd
13
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
14
f
H.
8.
i
nd
nd
39
10
3t
42
12
8
2t
15
11
137
2t
nd
nd
nd
nd
It
nd
It
nd
nd
22
o»
i
8
- ng/l
nd
nd
nd
nd
nd
nd
7
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
7
a
H*
tu
N
|
8
nd
nd
nd
207 t
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
207
V
3-
o
2
rt
n
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
63t
nd
nd
nd
nd
nd
nd
nd
nd
nd
63
f
o»
(n
CD
O
141
nd
nd
nd
nd
200
nd
100 1
nd
nd
nd
nd
nd
nd
7.xlO
nd
nd
nd
32t
nd
nd
nd
1.5x103
W
**
1
a
to
M
M
nd
nd
nd
69
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
69
ro
*>
1
o
^
H<
Ht
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
217
217
ro
V
Q
T»
PI
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
,,d
40 1
nd
nd
nd
nd
40
f
00
8.
5
nd
nd
nd
S
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
8
o
nd
nd
nd
2.8x10 t
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
40.X10
nd
21.X103
*nd » not detected
tbelow usual range of confident quantitatiou (Appendix II, Table 2).
*GLC peaks for all chemicals listed in Table 2, Appendix II, were monitored. Only chemicals detected and confirmed on two
or more GC columns are reported. Confirmation by thin layer was required, also, except at concentrations too low for spots to
be visualized.
-------
Table 45.
TRACE ORGANICS IN NORTH OUTFALL WATERS (SW-05, MOSQUITO CREEK), MUSKEGONj APR 74 TO DEC 75. J
Month
Apr
May
May
Jun-Jul
Jul
Aug
Sep
Oct
Nov.
Dec- Jan
Jsn
Feb
Mar
Apr
May
Jun
Jul
Aug
Sep
Oct
Nov
Dec
Detected
Compositing
period
(daily grab
samples)
4-8 to 4-30-74
5-1 to 5-14-74
5-15 to 5-31-74
6-1 to 7-11-74
7-12 to 7-31-74
7-31 to 8-29-74
8-30 to 9-30-74
10-1 to 10-29-74
10-30 to 12-1-74
12-2-74 to 1-6-75
1-6 to 1-31-75
2-4 to 2-28-75
3-4 to 3-31-75
4-1 to 4-30-75
5-2 to 6-2-75
6-2 to 7-2-75
7-2 to 7-30-75
8-2 to 9-3-75
9-2 to 10-2-75
10-2 to 11-4-75
11-4 to 11-28-75
12-2-75 to 1-2-76
means (ng/1)
Aldrin
nd*
nd
nd
14
nd
nd
nd
. nd
nd
nd
nd
ud
nd
nd
4t
nd
nd
nd
nd
nd
nd
nd
9
Dieldrin
nd
nd
nd
nd
31
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
31
i
g
W
7t
8t
8t
6t
6t
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
7
Heptachlor
nd
nd
nd
5t
47
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
5t
nd
nd
19
Heptachlor
epoxide
nd
nd
nd
nd
25
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
It
nd
13
an
p
nd
nd
nd
nd
145
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
145
S
0
nd
nd
25
nd
53
nd
nd
nd
112
lit
nd
4t
19
nd
nd
nd
nd
If
nd
nd
nd
nd
37
T
1
nd
nd
nd
nd
nd
nd
nd
46
nd
nd
nd '
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
46
Llndane
nd
nd
nd
11
37
nd
nd
84
375
nd
5t
2h
178
150
nd
nd
nd
It
nd
2t
nd
nd
84
Dlazlnon
nd
nd
nd
nd
nd
nd
48t
521
483
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
334
Atrazine
nd
nd
nd
nd
nd
nd
292xlOJ
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
292xl03
o
298
119t
183
415
625
nd
nd
lOOt
nd
350
nd
nd
nd
nd
359
33t
18t
nd
nd
nd
nd
25t
226
2,4-D(BE)d
nd
nd
nd
nd
203
nd
nd
nd
nd
nd
nd
nd
nd
650
195
nd
nd
nd
nd
nd
nd
nd
349
1
s-
K
nd
nd
nd
32
136
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
84
1
nd
r.d
15x10
lOxlO3
3x10 3t
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
115xl03
nd
nd
10x10
31.X103
*nd - not detected
tBelow usual range of confident quantttatlon (Appendix II, Table 2).
*GLC peaks for all chemicals listed in Table 2, Appendix II, were monitored. Only chemicals detected and confirmed on two
or .uore GC columns are reported, Confirmation by thin layer was required, also, except at concentrations too low for spots to
be visualized.
-------
Table 46. TRACE ORGANECS IN SOUTH OUTFALL WATERS (SW-34, BLACK CREEK), MUSKEGON, APR 74 TO DEC 75. t
VO
N3
Month
Apr
May
May
Jun-Jul
Jul
Aug
Sep
Oct
Nov
Dec- Jan
Jan
Feb
Mar
Apr
May
Jun
Jul
Aug
Sep
Oct
Nov
Dec
Detected
Compositing
period
(dally grab
samples)
4-8 to 4-30-74
5-1 to 5-14-74
5-15 to 5-31-74
6-1 to 7-11-74
7-12 to 7-31-74
?• ji to 8-29-74
8-30 to 9-30-74
10-1 to 10-29-74
10-30 to 12-1-74
12-2-74 to 1-6-75
1-6 to 1-31-75
2-4 to 2-28-75
3-4 to 3-31-75
4-1 to 4-30-75
5-2 to 6-2-75
6-2 to 7-2-75
7-2 to 7-30-75
8-2 to 9-2-75
9-2 to 10-2-75
10-2 to 11-4-75
11-4 to 11-28-75
17-2-75 to 1-2-76
means (ng/1)
>
M
a.
1
0
nd*
nd
nd
22
39
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
nd
30
fo
fr.
1
nd
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