EPA-660/2 74-016
February 1974
Environmental Protection Technology Series
Renovation of Secondary Effluent For
Reuse As A Water Resource
Office of Research and Development
U.S. Environmental Protection Agency
Washington, D.C. 20460
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RESEARCH REPORTING SERIES
Research reports of the Office of Research and
Monitoring, Environmental Protection Agency, have
been grouped into five series. These five broad
categories were established to facilitate further
development and application of environmental
technology. Elimination of traditional grouping
was consciously planned to foster technology
transfer and a maximum interface in related
fields. The five series are:
1. Environmental Health Effects Research
2. Environmental Protection Technology
3. Ecological Research
4. Environmental Monitoring
5. Socioeconomic Environmental Studies
This report has been assigned to the ENVIRONMENTAL
PROTECTION TECHNOLOGY series. This series
describes research performed to develop and
demonstrate instrumentation, equipment and
methodology to repair or prevent environmental
degradation from point and non-point sources of
pollution. This work provides the new or improved
technology required for the control and treatment
of pollution sources to meet environmental quality
standards.
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EPA-660/2-74-016
February 1974
RENOVATION OF SECONDARY EFFLUENT
FOR REUSE AS A WATER RESOURCE
By
Louis T. Kardos
William E. Sopper
Earl A. Myers
Richard R. Parizek
John B. Nesbitt
The Pennsylvania State University
University Park, PA 16802
Project 16080 DYJ (Formerly WPD 95-04)
Program Element 1BB045
Project Officer
Mr. Richard Thomas
Robert S. Kerr Environmental Research Laboratory
U.S. Environmental Protection Agency
Ada, Oklahoma 74820
Prepared for
OFFICE OF RESEARCH AND DEVELOPMENT
U.S. ENVIRONMENTAL PROTECTION AGENCY
WASHINGTON, D.C. 20460
For sale by the Superintendent of Documents, U.S. Government Printing Office. Washington. D.C. 20402
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EPA Review Notice
This report has been reviewed by the Environmental Protection
Agency 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 recommenda-
tion for use
11
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ABSTRACT
A 500,000 gallon per day supply of chlorinated, secondary treated
wastewater was applied through sprinkler irrigation systems to a com-
bined acreage of approximately 70 acres of cropland and forestland in
variously located experimental plots on Hublersburg silt loam or, clay
loam soils or on Morrison sandy loam soil. The hydraulic loads tested
ranged from one to six inches at weekly intervals. The effects of
application of th£ wastewater to the land on crop yields and crop
chemical composition were generally favorable for the two hydraulic
loads tested, 1 and 2 inches at weekly .intervals during the growing
season, only, or year-round. Harvested crops removed important amounts
of the two key eutropic nutrients, phosphorus and nitrogen. On the
forested sites tree growth response was beneficial except with red pine
on the Hublersburg soil when 2 inches of wastewater was applied at
weekly intervals during the growing season. N and P content of the
harvested crops and forest foliage was generally increased by waste-
water irrigation.
Nitrate nitrogen levels in water recharging through the soil at
the four foot depth were less than 10 mg/1 except in the growing- ,
season-2-inch red pine on Hublersburg soil and the year-round-2-inch
hardwood area on Marrison sandy loam soil when NC^-N values were 2 to
4 times the U.S.P.H.S. limit.
Phosphorus concentration in the suction lysimeter water samples
at a depth of four feet was no greater on wastewater treated areas
than on untreated control areas even on the sandy loam soil. Passage
through four feet of soil decreased P concentration 98 to 99% through
the combined effects of soil and vegetation in the "living filter"
system. Deep well samples adjacent to the Hublersburg soil area
showed no changes in water quality from normal background values.
One deep well completely surrounded by wastewater treated sandy loam
soil showed higher N0§ and Cl" concentrations in the fifth year of
treatment but still met U.S.P.H.S. drinking water standards.
Recharge benefit to two nearby university water supply wells
was estimated to result in-water table build-up equivalent to 2 to
6 feet after a 2 year period of recharge of 6.5 x 10? gallons per
year on 43.5 acres.
Annual costs of a spray irrigation system to recycle wastewater
through the land was estimated to range from $13 per year per E.D.U.
forlMGD to $8 per year per E.D.U. for 10MGD.
This report was submitted in fulfillment of Project No. 16080 DYJ
under the partial sponsorship of the Water Quality Office, Environ-
mental Protection Agency.
111
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CONTENTS
Section
I Conclusions 1
II Recommendations 5
III Introduction 7
IV Site Description and Experimental Procedures 11
V Irrigation System Operation 39
VI Cropland Aspects 99
VII Forested Areas 263
VIII Geohydrology 301
IX Design and Cost of Spray Irrigation Wastewater
Disposal System 383
X Acknowledgments 415
XI References 417
XII. Publications 427
XIII Appendices 431
v
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FIGURES
Page
1. The Waste Water Renovation and Conservation Cycle 3
2. Location of Waste Water Renovation and Conservation
Facilities and Network of Monitoring Wells and
Springs 10
3. Flow Diagram Schematic of University Waste Water
Treatment Plant 12
4. Water Table Contour Elevations in March, 1963 23
5. Water Table Contour Elevations in April, 1965 24
6. Layout of the Agronomy and Forestry Areas 26
7. Schematic Diagram of Various Types of Monitoring
Installations 28
8. Schematic Diagram of Trench Lysimeter 30
9. Oblique View of Trench Lysimeter. Irrigation Lines
in the Background Have a Two Percent Grade to
Provide Rapid Drainage to Prevent Freezing in the
Winter 31
10. Suction Lysimeter Equipment for Sampling Shallow
Soil Water (a) and Modified Equipment for Sampling
Deep Soil Water (b) 34
11. Monitoring Wells Drilled and Cased Below Streamlines
Containing Renovated Sewage Effluent. In Mapview
(b) Wells Appear to be Properly Located 36
12. Model I - 2 Inch. Rotor Sprinkler (11) 40
13. Model II - 1.5 Inch Rotor Sprinkler (11) 41
14. Indexed Position, Part-Circle Sprinkler, Rainbird
Model 35-PJ, Types E and F. (13) 43
15. Random Indexing, Grooved Deflector Sprinkler, Type C.
Upper Left View Shows Deflector; Lower Left View
Shows Sprinkler Position When Not Operating; Right
View Shows Sprinkler in Operating Position. (13) 44
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16. Surface Appearance with Various Degrees of Penetra-
tion of Snow by Effluent Applied with Different .,
Sprinklers 4b
17. Topographic Map of Research Area with Location of
Piezometer Sites, Irrigation Lines and V-Notch Weir 48
18. Profile Diagram of Hillside with Location of Piezometer
Sites 49
19. Shallow Well Water Level Elevations at Three Sites
Showing Typical Responses to Irrigation on 4/17/67
with Two Inches of Sewage Effluent 57
20. Cross Section of Hillside Showing Increase in Eleva-
tion of Perched Water Table (cross hatched area)
12 Hours After 2" Irrigation 48
21. Calculation of Water Storing Capacity of the Soil
Above the Perched Water Table for Sites 2 and 4 61
22. Water Level Elevations in Piezometers at Site 1 for
Two Observation Intervals, 1966-67 64
23. Water Level Elevations in Piezometers at Site 2 for
Two Observation Intervals, 1966-67 65
24. Water Level Elevations in Piezometers at Site 3 for
Two Observation Intervals, 1966-67 66
25. Water Level Elevations in Piezometers at Site 4 for
Two-Observation Intervals, 1966-67 67
26. Water Level Elevations in Piezometers at Site 5 for
Two Observation Intervals, 1966-67 68
27. Water Level Elevations in Piezometers at Site 6 for
Two Observation Intervals, 1966-67 69
28. Water Level Elevations in Piezometers at Site 7 for
Two Observation Intervals, 1966-67 70
29. Set of Piezometers at Site 1 Showing Limiting Perme-
ability, Perched Water Table, Water Levels in
Piezometers and Predicted Directions of Movement 72
30. Same as Figure 29 but at. Sites 2 and 3 73
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Page
31. Same as Figure 29 but at Sites 4 and 5 74
32. Same as Figure 29 but at Sites 6 and 7 7S
33. Piezometer Water Level Elevations (feet) at Several
Sites in 1966 . 77
34. Runoff Hydrograph for Interval Beginning on
May 15, 1967 81
35. Runoff Hydrograph for Interval Beginning on
May 23, 1967 82
36. Topographic Map with Seepage Areas Delineated by
Shading Two Days After Irrigation 84
37. Irrigation, Precipitation and Interflow Runoff at
Various Times After Start of Cycle II, Mar. -
Apr., 1967 87
\
38. Irrigation, Precipitation and Interflow Runoff at
Various Times After Start of Cycle III, June -
July, 1967 . 88
39. Piezometer Heads (P/W) vs. Hours After Start of 3-inch
Irrigation for All Stations and Depths During
Cycle I, Oct., 1966 90
40. Irrigation, Precipitation and Runoff During Cycle III,
Feb. - Mar., 1969 92
41. Plan of Strip Cropped Area 101
42. Regression of Removal Efficiency on Nitrogen Loading 144
43. Regression of Removal Efficiency on Phosphorus Loading 145
44. Nitrogen Added in Applied Sewage Effluent and Removed
in Harvested Reed Canarygrass and Silage Corn 149
45. Phosphorus Added in Applied Sewage Effluent and
Removed in Harvested Reed Canarygrass and Silage Corn 150
46. Diagram of (a) Suction Lysimeter with Single Hole
Stopper Assembly and (b) Lysimeter Installed at
Depth of 48 Inches with Tubing Inserted to Remove
Sample 154
viii
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47. Mfean Annual Phosphorus Concentration in Suction
Lysimeters at the Six Inch Depth in the Corn
Rotation Area Receiving 0, 1, and 2 Inches of
Wastewater at Weekly Intervals, Apr. - Nov., 1965-
1969 157
48. Mean Annual Phosphorus Concentration in Suction
Lysimeters at the 24-Inch Depth in the Corn
Rotation Area Receiving 0, 1, and 2 Inches of
Wastewater at Weekly Intervals, Apr. - Nov., 1965-
1969 158
49. Msan Annual Phosphorus Concentration in Suction
Lysimeters at the 48-Inch Depth in the Corn
Rotation Area Receiving 0, 1, and 2 Inches of
Wastewater at Weekly Intervals, Apr. - Nov., 1965-
1969 159
50. Nitrate-N in Suction Lysimeters at the 48-Inch Depth
in the Corn Rotation and Reed Canarygrass Areas 161
51. Mean Annual Concentration of Various Chemical Constit-
uents in Suction Lysimeter Samples at the 48-Inch
Depth in the Reed Canarygrass and Corn Rotation
Areas in 1969 165
52. Effect of Various Wastewater Levels on the Corn
Rotation Area on Exchangeable Cations Averaged Over
Five One-Foot Depth Intervals and Over Six Sampling
Years, 1963, 1965-1969. Bars Having a Common Letter
for Any Constituent Are Not Significantly Different.
P = 0.01 196
53. Exchangeable ^fegnesium at One-Foot Depth Intervals in
the Corn Rotation Area Averaged Over Six Sampling
Years, 1963, 1965-1969. Bars Having a Common Letter
at Any Depth Are Not Significantly Different. P = 0.01 197
54. Exchangeable Sodium at One-Foot Depth Intervals in the
Corn Rotation Area Averaged Over Six Sampling Years,
1963, 1965-1969. Bars Having a Common Letter at Any
Depth Are Not Significantly Different. P = 0.01 198
55. Soil pH at One-Foot Depth Intervals in the Corn Rotation
Area Averaged Over Six Sampling Years, 1963, 1965-1969.
Bars Having a Common Letter at Any Depth Are Not
Significantly Different. P = 0.01 200
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56. Exchangeable Msmganese at One-Foot Depth Intervals in
the Corn Rotation Area Averaged Over Six Sampling
Years, 1963, 1965-1969. Bars Having a Common Letter
at Any Depth Are Not Significantly Different. P = 0.01 ^01
57. Extractable Chloride at One-Foot Depth Intervals in
the Corn Rotation Area Averaged Over Six Sampling
Years, 1963, 1965-1969. Bars Having a Common Letter
at Any Depth Are Not Significantly Different. P = 0.01 202
58. Phosphorus Adsorption Data for H202-Treated and Un-
treated Soil, 0-12 inches, Plotted According to the
Langmuir Equation (8) 223
59. Phosphorus Adsorption Data for H202- Treated and Un-
treated Soil, 12-24 inches, Plotted According to the
Langmuir Equation (8) 224
60. Phosphorus Adsorption Data for ^02- Treated and Un-
treated Soil,,, 24-36 inches, Plotted According to the
Langmuir Equation (8) 225
~f
61. Phosphorus Adsorption Data for H202-Treated and Un-
treated Soil, 36-48 inches, Plotted According to the
Langmuir Equation (8) 226
62. Phosphorus Adsorption Data for H202-Treated and Un-
treated Soil, 48-60 inches, Plotted According to the
Langmuir Equation (8) 227
63. Phosphorus Adsorption Data for H202-Treated and Un-
treated Soil, 0-12 inches, Plotted According to the
Freundlich Equation (8) 229
64. Phosphorus Adsorption Data for ^02- Treated and un-
treated Soil, 12-24 inches, Plotted According to the
Freundlich Equation (8) 230
65. Phosphorus Adsorption Data for ^02 -Treated and Un-
treated Soil, 24-36 inches, Plotted According to the
Freundlich Equation (8) 231
66. Phosphorus Adsorption Data for ^02- Treated and Un-
treated Soil, 36-48 inches, Plotted According to the
Freundlich Equation (8) 232
67. Phosphorus Adsorption Data for H202-Treated and Un-
treated Soil, 48-60 inches, Plotted According to the
Freundlich Equation (8)
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68. Platinum Microelectrodes and Oxygen Concentration
Chambers 254
69. Mean Annual Phosphorus Concentration in Suction
Lysimeter Samples at Three Depths in the Hardwood
Area on Hublersburg Soil Which Received One Inch of
Wastewater at Weekly Intervals. 1965-1969 267
70. Msan Annual Phosphorus Concentration in Suction
Lysimeter Samples at Three Depths in the Red Pine
Area on Hublersburg Soil Which Received One Inch of
Wastewater at Weekly Intervals. 1965-1969 268
71. Mean Annual Phosphorus Concentration in Suction
Lysimeter Samples at Three Depths in the Red Pine
Area on Hublersburg Soil Which Received Two Inches
of Wastewater at .Weekly Intervals. 1965-1969 269
72. Mean Annual Phosphorus Concentration in Suction
Lysimeter Samples at Three Depths in the Old Field
Area on Hublersburg Soii Which Received Two Inches
of Wastewater at Weekly\Intervals. 1965-1969 270
73. Msan Annual Nitrate-Nitrogen Concentration in Suction
Lysimeter Samples at the 48-inch Depth on Various
Forest Areas. 1965-1969 280
74. Mean Annual MBAS Concentration in Suction Lysimeter
Samples at Three Depths and in the Applied Waste-
water in the Hardwood -Area on Hublersburg Soil Which
Received Four Inches of Wastewater Weekly. 1963-1968 283
75. Msan Annual Phosphorus Concentration in Suction
Lysimeter Samples at Three Depths and in the Applied
Wastewater in the Hardwood Area on Hublersburg Soil
Which Received Four Inches of Wastewater Weekly.
1963-1968 284
76.. Msan Annual Nitrate-Nitrogen Concentration in Suction
Lysimeter Samples at Three Depths in the Hardwood
Area on Hublersburg Soil Which Has Received Four
Inches of Wastewater Weekly. 1963-1968 285
77. Percent of UN-14 Deep Well Samples with Chloride
Concentrations Equalling or Exceeding Stated Values 305
78. Percent of UN-14 Deep Well Samples with N03-N Concen-
trations Equalling or Exceeding Stated Values 307
XI
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79. Percent "of UN-14 Deep Well Samples with ABS Concen-
trations Equalling or Exceeding Stated Values 308
80. Percent of UN-14 Deep Well Samples with P Concentra-
tions Equalling or Exceeding Stated Values 309
81. Percent of F-3 Deep Well Samples with P Concentrations
Equalling or Exceeding Stated Values 310
82. Percent of F-3 Deep Well Samples with ABS Concentra-
tions Equalling or Exceeding Stated Values 311
83. Percent of F-3 Deep Well Samples with N03-N Concen-
trations Equalling or Exceeding Stated Values 312
84. Percent of F-3 Deep Well Samples with Chloride Concen-
trations Equalling or Exceeding Stated Values 314
85. Percent of F-4 Deep Well Samples with Chloride Concen-
trations Equalling or Exceeding Stated Values 315
86. Percent of F-4 Deep Well Samples with NCU-N Concentra-
tions Equalling or Exceeding Stated Values 316
87. Percent of F-4 Deep Well Samples with ABS Concentra-
tions Equalling or Exceeding Stated Values 318
88. Percent of F-4 Deep Well Samples with P Concentrations
Equalling or Exceeding Stated Values 319
89. Percent of F-5 Deep Well Samples with Chloride Concen-
trations Equalling or Exceeding Stated Values 320
90. Percent of F-5 Deep Well Samples with NO^-N Concentra-
tions Equalling or Exceeding Stated Values 321
91. Percent of F-5 Deep Well Samples with P Concentrations
Equalling or Exceeding Stated Values 322
92. Percent of F-5 Deep Well Samples with ABS Concentra-
tions Equalling or Exceeding Stated Values 323
93. Percent of G-3 Deep Well Samples with Chloride Concen-
trations Equalling or Exceeding Stated Values 332
94. Percent of G-3 Deep Well Samples with N03-N Concentra-
tions Equalling or Exceeding Stated Values
333
XII
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Page
95. Percent of G-3 Deep Well Samples with ABS Concentra-
tions Equalling or Exceeding Stated Values 335
96. Percent of Deep Trench Lysimeter (SGL) Samples at the
Five-foot Depth With Chloride Concentrations
Equalling or Exceeding Stated Values 337
97. Percent of Deep Trench Lysimeter (SGL) Samples at the
Ten-foot Depth With Chloride Concentrations
Equalling or Exceeding Stated Values 338
98. Percent of Deep Trench Lysimeter (SGL) Samples at the
14-foot Depth With Chloride Concentrations
Equalling or Exceeding Stated Values 339
99. Percent of Deep Trench Lysimeter (SGL) Samples at the
Five-foot Depth With NOj-N Concentrations Equalling
or Exceeding Stated Values 341
100. Percent of Deep Trench Lysimeter (SGL) Samples at the
Ten-foot Depth With NOyN Concentrations Equalling
or Exceeding Stated Values 342
101. Percent of Deep Trench Lysimeter (SGL) Samples at the
14-foot Depth With N03-N Concentrations Equalling
or Exceeding Stated Values 343
102. Percent of Deep Trench Lysimeter (SGL) Samples at the
Five-foot Depth With P Concentrations Equalling or
Exceeding Stated Values 344
103. Percent of Deep Trench Lysimeter (SGL) Samples at the
Ten-foot Depth With P Concentrations Equalling or
Exceeding Stated Values 345
104. Percent of Deep Trench Lysimeter (SGL) Samples at the
14-foot Depth With P Concentrations Equalling or
Exceeding Stated Values 346
105. Percent of Deep Trench Lysimeter (SGL) Samples at the
Five-foot Depth With ABS Concentrations Equalling
or Exceeding Stated Values 348
106. Percent of Deep Trench Lysimeter (SGL) Samples at the
Ten-foot Depth With ABS Concentrations Equalling
or Exceeding Stated Values 349
xiii
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107. Percent of Deep Trench Lysimeter (SGL) Samples at the
14-foot Depth With ABS Concentrations Equalling or
Exceeding Stated Values 350
108. Percent of Deep Suction Lysimeter (SLG-1) Samples at
the Six-foot Depth With P Concentrations Equalling
or Exceeding Stated Values 352
109. Percent of Deep Suction Lysimeter (SLG-1) Samples at
the 17.5-foot Depth With P Concentrations Equalling
or Exceeding Stated Values 353
110. Percent of Deep Suction Lysimeter (SLG-1) Samples at
the Six-foot Depth With ABS Concentrations Equalling
or Exceeding Stated Values 355
111. Percent of Deep Suction Lysimeter (SLG-1) Samples at
the 17.5-foot Depth With ABS Concentrations Equalling
or Exceeding Stated Values 356
112. Percent of Deep Suction Lysimeter (SLG-1) Samples at
the Six-foot Depth With Chloride Concentrations
Equalling or Exceeding Stated Values 358
113. Percent of Deep Suction Lysimeter (SLG-1) Samples at
the 17.5-foot Depth With Chloride Concentrations
Equalling or Exceeding Stated Values 359
114. Percent of Deep Suction Lysimeter (SLG-1) Samples at
the Six-foot Depth With N03-N Concentrations
Equalling or Exceeding Stated Values 360
115. Percent of Deep Suction Lysimeter (SLG-1) Samples at
the 17.5-foot Depth With N03-N Concentrations
Equalling or Exceeding Stated Values 361
116. Water Level Declines -in Selected Wells 367
117. Rainfall Deficit and Water Level Decline Within the
Gatesburg Aquifer Due to Natural Depletion 376
118. Pumping and Non-Pumping Water Levels Related to Decline
in Well Yields Within the university Well Field 377
119. Power Requirements for Pumping 1000 Gallons of Water
Per Minute at a 100-foot Head for Various Wire to
Water Efficiencies (109) 380
xiv
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120. Land Requirements and Costs with and without a Buffer
Zone Related to Daily Flow and Application Rates 390
121. Sprayfield Sprinkler Arrangements 391
122. Required Sprinkler Separation Distances in Relation
to Effective Distribution Diameter with Three Types
of Spacing 393
123. Nunfoer of Sprinklers per Acre in Relation to Effective
Distribution Diameter with Three Types of Spacing 394
124, Sprinkler Discharge for Various Effective Distribution
Diameters and a 1/4 Inch per Hour Application Rate 396
125. Sprinkler Discharge for Various Effective Distribution
Diameters and a 1/6 Inch per Hour Application Rate 397
126. Instantaneous Discharge (gpm/acre) for Various Applica-
tion Rates 398
127. Required Lengths of Lateral Pipeline for Various
Effective Distribution Diameters 399
128. Lateral Flow in Relation to Daily Flow, Application
Rate and Side Dimension Ratio of the Irrigation Plot 400
129. Required Lengths of Lateral Pipeline in Relation to
Daily Flow, Application Rate and Side Dimension
Ratio of the Irrigation Plot 401
130. Lateral or Header Diameters for Various Lateral or
Header Flows as Related to Pipe Length and Allowable
Headloss 403
131. Headloss for Various Flows and Pipe Diameters 404
132. Capital and Annual Cost Distribution for a 1 MGD Spray
Irrigation Wastewater Disposal System 411
133. Annual Cost of Spray Irrigation Wastewater Disposal
System per Thousand Gallons for Various Daily Flows 412
134. Annual Cost of Spray Irrigation Wastewater Disposal
System per Equivalent Dwelling Unit (EDU) for
Various Daily Flows 413
xv
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TABLES
No.
1 Composition of Sewage Effluent
2 Composition of Applied Effluent Expressed as a
Fertilizer Equivalent Formula, N:P:K, at a Rate of
1000 Ib per Acre 15
3 Monitored Irrigation Areas and Application System
Parameters, 1963-1969 17
4 Summary of Uniformity Coefficients from Rotor Design
Tests 42
5 Average Infiltration Rates at Sites 1-7, in Inches per
Hour 50
6 Average Percolation Rates (inches per hour) at Six Inch
Intervals to Depths Listed at Sites 1-7 50
7 Average Aeration Porosity (Percent by Volume) at 50 on
Water Tension at Six Inch Intervals to Depths Listed
at Sites 1-7 51
8 Bulk Density (grams per cc) at Six Inch Intervals to
Depths Listed at Sites 1-7 52
9 Percentages of Total Porosity, Porosity from 175 to 10
Microns and from 10 to 0.10 Microns in Diameter for
Sites 1-7 at the Given Depth Intervals 53
10 Shallow Well Elevations for Sites 1-7 on April 17-21,
1967 56
11 Time in Hours After Termination of Irrigation for Shallow
Well Readings Presented in Table 10 56
12 Water Level Elevations (feet) with Respect to Irrigation
and Rainfall at Sites 1-7 59
13 Total Declines in Water Levels of Shallow Wells in Feet
and Order of Rapidity of Decline in Water Levels by
Sites 1-7 60
14 Aeration Porosity and Water Storage Values (Inches) for
Six-Inch Depth Increments in the Soils at Sites 2 and 4 62
xvi
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No.
15 Soil Permeabilities Determined on July 11, 1967 by the
Piezometric Method for All Piezometers at Sites 1-7 63
16 Correlation Coefficients Relating Soil Permeability and
Various Soil Properties 63
17 Peak Water Level Elevations for Shallow Wells and
Piezometers for the Interval 1/2 - 1/6/67 at Sites 1-7 71
18 Surface Runoff Expressed as Peak Discharge (gpm per acre),
Total Discharge (gal./acre), and Percent of the Total
Application for the Indicated Dates 78
19 Soil Temperatures Averaged for 7 Sites at Various Depths
Before and After Irrigation for Examples A, B, and C 79
20 Effects of Air Temperature and Soil Frost Conditions on
Surface Runoff for Three Irrigation Applications 80
21 Total Duration of Runoff from 2-Inch Irrigation and
Duration After Termination of Irrigation 80
22 Phosphorus Content in Applied Effluent, in a 6 In.
Suction Lysimeter, and in Total Runoff at Different
Times Expressed as Hours After Irrigation Had
Terminated 83
23 Percentage of Irrigation Amount Appearing as Runoff (R/I)
and Inches of Total Precipitation which Occurred During
the Week Prior to Irrigation for all Cycles 86
24 Average Peak Pressure Heads in Piezometers for the Six
Runs and the Three Cycles ~-~- 89
25 Sequences, Areas Irrigated and Dates of Each Irrigation
Cycle 93
26 Percentage of Effluent Volume Applied Appearing as
Runoff during the Minimun and Maximum Sequences for
Five Irrigation Cycles 94
27 Peak Runoff Rates Relative to Irrigation Application
Rates during the Minimum and Maximum Sequences for the
Five Irrigation Cycles 94
28 Maximum Air Temperatures and Peak Rates of Runoff
Relative to Irrigation Application Rates for Cycles II
and III 95
xvii
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No. Page.
29 Concentrations in Parts Per Million of Phosphorus and
Nitrogen and Percent Change in Concentration in
Watershed Runoff at Four Sampling Times for Four
Irrigation Cycles 96
30 Crop Potation Sequence 102
31 Irrigation Program for Agronomy Areas 103
32 Crop Yields and Percentage Increase in Yields at Various
Levels of Sewage Effluent Application - 1963 105
33 Crop Yields and Percentage Increase in Yields at Various
Levels of Sewage Effluent Application - 1964 106
34 Crop Yields and Percentage Increase in Yields at Various
Levels of Sewage Effluent Application - 1965 107
35 Crop Yields and Percentage Increase in Yields at Various
Levels of Sewage Effluent Application - 1966 108
36 Crop Yields and Percentage Increase in Yields at Various
Levels of Sewage Effluent Application - 1967 109
37 Crop Yields and Percentage Increase in Yields at Various
Levels of Sewage Effluent Application - 1969 110
38 Yields of Reed Canarygrass Receiving Two Inches of
Sewage Effluent Per Week - 1965-1969 111
39 Normal Monthly Precipitation and Deviations from the
Normal - Inches 111
40 Average Nutrient Composition of Red Clover Hay Receiving
Various Levels of Sewage Effluent Per Week. 1963-1964 112
41 Average Nutrient Composition of Alfalfa Hay Receiving
Various Levels of Sewage Effluent Per Week, 1963,
1965-1967 113
42 Average Nutrient Composition of Crops Receiving Various
Levels of Sewage Effluent Per Week - 1963 114
43 Average Nutrient Composition of Crops Receiving Various
Levels of Sewage Effluent Per Week - 1964 115
XVlll
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No.
44 Average Nutrient Composition of Crops Receiving Various
Levels of Sewage Effluent Per Week - 1965
45 Average Nutrient Composition of Crop's Receiving Various
Levels of Sewage Effluent Per Week - 1966 117
46 Average Nutrient Composition of Crops Receiving Various
Levels of Sewage Effluent Per Week - 1967 118
47 Average Nutrient Composition of Crops Receiving Various
Levels of Sewage Effluent Per Week - 1969 119
48 Average Nutrient Composition of Reed Canarygrass
Receiving Two Inches of Sewage Effluent Per Week.
1965-1969 120
49 Quantities of Nutrients (Pounds Per Acre) Removed by
Red Clover Receiving Various Levels of Sewage Effluent
Per Week. 1965-1964 122
50 Quantities of Nutrients (Pounds Per Acre) Removed by
Alfalfa Receiving Various Levels of Sewage Effluent
Per Week. 1963, 1965-1967 123
51 Quantities of Nutrients (Pounds Per Acre) Removed by
Crops Receiving Various Levels of Sewage Effluent Per
Week - 1963 124
52 Quantities of Nutrients (Pounds Per Acre) Removed by
Crops Receiving Various Levels of Sewage Effluent Per
Week - 1964 125
53 Quantities of Nutrients (Pounds Per Acre) Removed by
Crops Receiving Various Levels of Sewage Effluent Per
Week - 1965 126
54 Quantities of Nutrients (Pounds Per Acre) Removed by
Crops Receiving Various Levels of Sewage Effluent Per
Week - 1966 127
55 Quantities of Nutrients (Pounds Per Acre) Removed by
Crops Receiving Various Levels of Sewage Effluent Per
Week - 1967 128
56 Quantities of Nutrients (Pounds Per Acre) Removed by
Crops Receiving Various Levels of Sewage Effluent Per
Week - 1969 129
xix
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No. Pag£
57 Quantities of Nutrients (Pounds Per Acre) Removed by
Reed Canary-grass Receiving Two Inches of Sewage
Effluent Per Week. 1965-1969 130
58 Average Concentration (mg/1) of Various Constituents in
Wastewater Applied to the Rotation Crops at Rates of
One and Two Inches Per Week - 1963-1969 131
59 Average Concentration (mg/1) of Various Constituents
Applied to the Reed Canarygrass Area - 1965-1969 133
60 Total Amounts (Pounds Per Acre) of Various Constituents
in Sewage Effluent Applied to the Rotation Crops at
Rates of One and Two Inches Per Week - 1963-1969 134
61 Total Amounts (Pounds Per Acre) of Various Constituents
Applied to Reed Canarygrass Receiving Two Inches of
Sewage Effluent Weekly - 1965-1969 136
62 Renovation Efficiency (Percent) of Crops at One and Two
Inch Per Week Applications - 1963 137
63 Renovation Efficiency (Percent) of Crops at One and Two
Inches Per Week Applications - 1964 138
64 Renovation Efficiency (Percent) of Crops at One and Two
Inches Per Week Applications - 1965 139
65 Renovation Efficiency (Percent) of Crops at One and Two
Inches Per Week Applications - 1966 140
66 Renovation Efficiency (Percent) of Crops at One and Two
Inches Per Week Applications - 1967 141
67 Renovation Efficiency (Percent) of Crops at One and Two
Inches Per Week Applications - 1969 142
68 Renovation Efficiency (Percent) of Reed Canarygrass at
Two Inches of Sewage Effluent Application - 1965-1969 143
69 Average Removal Efficiencies of Various Crops of Nitrogen
and Phosphorus in Comparable Years 146
70 Amounts Removed in Harvested Crops Per Acre Per Crop
Year on Wastewater Treated Areas - 1963-1969 147
xx
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No..
71 Mean Annual Concentration (mg/1) of Phosphorus in
Suction Lysimeter Samples at Three Depths in Corn
Rotation Area Receiving Various Levels of Wastewater.
1965-1969 166
72 Mean Annual Concentration (mg/1) of Nitrate Nitrogen in
Suction Lysimeter Samples at Three Depths in Corn
Rotation Area Receiving Various Levels of Wastewater.
1965-1969 167
73 Mean Annual Concentration (mg/1) of Kjeldahl Nitrogen in
Suction Lysimeter Samples at Three Depths in Corn
Rotation Area Receiving Various Levels of Wastewater.
1965-1969 168
74 Mean Annual Concentration (mg/1) of Ammonium Nitrogen in
Suction Lysimeter Samples at Three Depths in Corn
Rotation Area Receiving Various Levels of Wastewater.
1968-1969 169
75 Mean Annual Concentration (mg/1) of Potassium in Suction
Lysimeter Samples at Three Depths in Corn Rotation
Area Receiving Various Levels of Wastewater. 1965-
1969 170
76 Mean Annual Concentration (mg/1) of Calcium in Suction
Lysimeter Samples at Three Depths in Corn Rotation
Area Receiving Various Levels of Wastewater. 1965-
1969 171
77 Mean Annual Concentration (mg/1) of Magnesium in Suction
Lysimeter Samples at Three Depths in Corn Rotation
Area Receiving Various Levels of Wastewater. 1965-
1969 172
78 Mean Annual Concentration (mg/1) of Sodium in Suction
Lysimeter Samples at Three Depths in Com Rotation
Area Receiving Various Levels of Wastewater. 1965-
1969 173
*
79 Mean Annual Concentration (mg/1) of Chloride in Suction
Lysimeter Samples at Three Depths in Com Rotation
Area Receiving Various Levels of Wastewater. 1965-
1969 174
80 Mean Annual Concentration (mg/1) of Manganese in Suction
Lysimeter Samples at Three Depths in Corn Rotation
Area Receiving Various Levels of Wastewater. 1965-
1969 175
xxi
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No.
81 Mean Annual Concentration (mg/1) of Boron in Suction
Lysimeter Samples at Three Depths in Corn Rotation
Area Receiving Various Levels of Wastewater. 1965-
1969 176
82 Mean Annual pH in Suction Lysimeter Samples at Three
Depths in Corn Rotation Area Receiving Various
Levels of Wastewater. 1965-1969 177
83 Mean Annual Concentration (mg/1) of MBAS in Suction
Lysimeter Samples at Three Depths in Corn Rotation
Area Receiving Various Levels of Wastewater. 1965-
1969 178
84 Mean Annual Concentration (mg/1) of Various Constituents
in Suction Lysimeter Samples at Three Depths in the
Reed Canarygrass Area Receiving Two Inches of
Wastewater Weekly. 1966-1969 179
85 The Effect of Years on Mean Annual Concentration (mg/1)
of Phosphorus in Suction Lysimeter Samples at Three
Depths in the Corn Rotation Area Segregated by
Wastewater Treatment Level. 1965-1969 180
86 The Effect of Years on Mean Annual Concentration (mg/1)
of Nitrate Nitrogen in Suction Lysimeter Samples at
Three Depths in the Corn Rotation Area Segregated by
Wastewater Treatment Level. 1965-1969 181
87 The Effect of Years on Mean Annual Concentration (mg/1)
of Kjeldahl Nitrogen in Suction Lysimeter Samples at
Three Depths in the Corn Rotation Area Segregated by
Wastewater Treatment Level. 1965-1969 182
88 The Effect of Years of Mean Annual Concentration (mg/1)
of Ammonium Nitrogen in Suction Lysimeter Samples at
Three Depths in the Corn Rotation Area Segregated by
Wastewater Treatment Level. 1968-1969 183
89 The Effect of Years on Mean Annual Concentration (mg/1)
of Potassium in Suction Lysimeter Samples at Three
Depths in the Com Rotation Area Segregated by
Wastewater Treatment Level. 1965-1969 184
90 The Effect of Years on Mean Annual Concentration (mg/1)
of Calcium in Suction Lysimeter Samples at Three
Depths in the Corn Rotation Area Segregated by
Wastewater Treatment Level. 1965-1969 185
200.1
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No.
91 The Effect of Years on Mean Annual Concentration (mg/1)
of Magnesium in Suction Lysimeter Samples at Three
Depths in the Corn Rotation Area Segregated by
Wastewater Treatment Level. 1965-1969 186
92 The Effect of Years on Mean Annual Concentration (mg/1)
of Sodium in Suction Lysimeter Samples at Three
Depths in the Corn Rotation Area Segregated by
Wastewater Treatment Level. 1965-1969 187
93 The Effect of Years on Mean Annual Concentration (mg/1)
of Chloride in Suction Lysimeter Samples at Three
Depths in the Corn Rotation Area Segregated by
Wastewater Treatment Level. 1965-1969 " 188
94 The Effect of Years on Mean Annual Concentration (mg/1)
of Manganese in Suction Lysimeter Samples at Three
Depths in the Corn Rotation Area Segregated by
Wastewater Treatment Level. 1965-1969 189
95 The Effect of Years on Mean Annual Concentration (mg/1)
of Boron in Suction Lysimeter Samples at Three Depths
in the Com Rotation Area Segregated by Wastewater
Treatment Level. 1965-1969 190
96 The Effect of Years on Mean Annual pH in Suction
Lysimeter Samples at Three Depths in the Corn Rotation
Area Segregated by Wastewater Treatment Level. 1965-
1969 191
97 The Effect of Years on Mean Annual Concentration (mg/1)
of MBAS in Suction Lysimeter Samples at Three Depths
in the Corn Rotation Area Segregated by Wastewater
Treatment Level. 1965-1969 192
98 Chemical Characteristics of Soil Samples at Five Depths
from Plots of the Com Rotation Area Receiving Various
Levels of Wastewater. 1963 205
99 Chemical Characteristics of Soil Samples at Five Depths
from Plots of the Com Rotation Area Receiving Various
Levels of Wastewater. 1965 206
100 Chemical Characteristics of Soil Samples at Five Depths
from Plots of the Corn Rotation Area Receiving Various
Levels of Wastewater. 1966 207
xxm
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No.
101 Chemical Characteristics of Soil Samples at Five Depths
from Plots of the Corn Rotation Area Receiving Various
Levels of Wastewater. 1967 208
102 Chemical Characteristics of Soil Samples at Five Depths
from Plots of the Corn Rotation Area Receiving Various
Levels of Wastewater. 1968 209
103 Chemical Characteristics of Soil Samples at Five Depths
from Plots of the Corn Rotation Area Receiving Various
Levels of Wastewater. 1969 210
104 Chemical Characteristics of Soil Samples at Five Depths
from the Reed Canarygrass Area Which Received Two
Inches of Wastewater Per Week. 1969 211
105 Chemical Characteristics of Soil Samples at Five Depths
from Plots of the Hardwood Area on Morrison Sandy
Loam Soil at the Gamelands Which Received 0 and 2
Inches of Wastewater Weekly. 1967 212
106 Chloride Content of Soil Samples at Five Depths from
Plots of the Corn Rotation Area Receiving Various
Levels of Wastewater 213
107 Boron Content of Soil Samples at Five Depths from Plots
of the Corn Rotation Area Receiving Various Levels of
Wastewater. 214
108 Nitrogen and Organic Matter Content of Soil Samples at
Five Depths from Plots of the Corn Rotation Area
Receiving Various Levels of Wastewater 215
109 Physical and Chemical Characteristics of Soil Samples
from Control Plots of the Corn Rotation Area 220
110 Equilibrium Concentration (mmole/fc) and Phosphorus
Adsorbed (mg/g) by Untreated Soil from Various Depths 221
111 Equilibrium Concentration (mmole/£) and Phosphorus
Adsorbed (mg/g) by Treated Soil from Various Depths 222
112 Phosphorus Langmuir Adsorption Maxima (ug/g) of
Untreated and Treated Soil in Relation to Depth 228
113 Phosphorus Adsorbed in an Equilibrium Concentration of
100 mg P/l as Determined from the Freundlich Adsorption
Isotheims 234
xxiv
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No.
114 Bray Phosphorus (yg/g) in Soil Samples Obtained in
Different Years at Five Depths from Plots Receiving
Various Levels of Wastewater Applications 235
115 Mean Yield and Boron Content of Beans Grown in Field
Plots Receiving Various Levels of Wastewater. 1967 239
116 Average Concentration of Boron (mg/1) in Lysimeter
Samples During Irrigation (adsorption) and Non-
Irrigation (desorption) Periods, 1967-1968 239
117 Average Plant Weights and Chemical Composition of Bean
Plants from Greenhouse Experiment- -Control Area Soil 242
118 Average Plant Weights and Chemical Composition of Bean
Plants from Greenhouse Experiment- -One Inch Area Soil 243
119 Average Plant Weights and Chemical Composition of Bean
Plants from Greenhouse Experiment --Two Inch Area Soil 244
120 Effect of Boron Treatment and Source of Soil on Dry
Weight (grams) of Bean Plants in Greenhouse Experiment 245
121 pH and Water Soluble Manganese Content of Soil from Pots
Used in Greenhouse Study 246
122 Effect of Boron Treatment and Source of Soil on Boron
Content (yg/g) of Bean Plants in Greenhouse Experiment 247
123 Autoclave-Extractable Boron Content of Soil Materials
Used in Greenhouse Experiment --yg/g 248
124 Boron Adsorbed by the Soil Materials Equilibrated with
the 5.0 mg/1 Solution 249
125 Dithionate-Citrate Extractable Fe^ and Boron Adsorptive
Capacity of the Nine Soil Materials from the Three
Wastewater Treatments 250
126 Ranked Means in Ascending Order of the Main Factors of
Oxygen Diffusion Rate Experiment 257
127 Ranked Means of the Main Factors of the Oxygen Concentra-
tion Experiment 258
128 Concentration of Various Forms of Nitrogen and of
Manganese and Iron in Soil Water Samples 259
XXV
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No..
129 The Crop x Effluent Interaction with Respect to Nitrate
Nitrogen Levels in Suction Lysimeter Samples Averaged
Over Both Depths 260
130 Chemical Composition of Sewage Effluent Applied on the
Experimental Plots (Farm Woodlot Site) During the
Period April 15, 1969 to October 29, 1969 264
131 Average Concentration of Constituents in the Percolate
Water Samples Collected from Tension Lysimeters in the
Effluent Treated Plots at the Farm Woodlot Site During
the Irrigation Period April 15 to October 29, 1969 265
132 Average Concentration of Constituents in the Percolate
Water Samples Collected from Tension Lysimeters in the
Control Plots at the Farm Woodlot Site During the
Period April 15 to October 29, 1969 272
,;*
133 Average Concentration of Percolate Samples Collected from
Forest Floor Pans and Tension Lysimeters in the New Red
Pine 2" Per Week Area During the Irrigation Period
4-15-69 to 10-29-29 274
134 Average Concentration in Percolate Samples Collected from
Forest Floor Pans and Tension Lysimeters in the New
Gamelands Area Which Received 2" of Effluent Per Week
.During the Period 1-1-69 to 12-31-69 276
135 Average Concentration in Percolate Samples Collected from
Forest Floor Pans and Tension Lysimeters in the Control
Plot at the New Gamelands Site During the Period
1-1-69 to 12-31-69 277
136 Mean Annual Concentration (mg/1) of Nitrate-Nitrogen in
Suction Lysimeter Samples at Three Depths in Forest
Areas Receiving Various Levels of Wastewater. 1965-
1969 278
137 Average Concentration of Constituents in the Applied
Sewage Effluent and in the Percolate Water Samples
Collected from Pan Lysimeters Located in the Hardwood
Plot Which Received 4 Inches of Effluent Per Week
During the Period April 15 to October 14, 1968 281
138 Mean Concentration of Chemical Elements in the Soil
Samples Collected in 1963, 1964, and 1965 in the
Hardwood 1-Inch Treatment and Control Plots 287
xxvi
-------
No.
139 Msan Concentration of Chemical Elements in the Soil
Samples Collected in 1965 in the Hardwood 4-Inch
Treated Plot 289
140 Average Chemical Content of Tree Foliage and Old Field
Ground Vegetation at the End of the 1965 Irrigation
Season 291
141 Average Chemical Content of Tree Foliage and Old Field
Ground Vegetation at the End of the 1966 Irrigation 292
Season
142 Average Chemical Content of Tree Foliage and Old Field
Ground Vegetation at the End of the 1967 Irrigation 293
Season
143 Average Annual Diameter Growth for Period 1964 to 1969 295
144 Average Annual Terminal Height Growth in the Red Pine
Plots During the Period 1963 to 1968 296
145 Average Annual Height Growth of White Spruce 296
146 Growth Response of Ground Vegetation in the Open White
Spruce Plots, Expressed in Terms of Dry Matter
Production 297
147 Survival of Planted Tree Seedlings - 1965-1969 298
148 Average Total Height Growth of Surviving Seedlings in
the First Year, 1965, and in 1969 299
149 Phosphorus in Monitoring Wells 326
150 Nitrate-N in Monitoring Wells 327
151 Chloride in Monitoring Wells 328
152 Chloride Concentrations Equalled or Exceeded by 20%,
50%, and 80% of the Values for 5, 10, and 14 foot
Depths in the Gameland's Trench Lysimeter (SGL) 336
153 Nitrate-Nitrogen Concentrations Equalled or Exceeded by
20%, 50%, and 80% of the Values for 5, 10, and 14-foot
Depths in the Gameland's Trench Lysimeter (SGL) 340
xxvii
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No.
154 Phosphorus Concentrations Equalled or Exceeded by 20%
50%, and 80% of the Values for 5, 10, and 14 foot
Depths in the Gameland's Trench Lysimeter (SGL) 347
155 ABS Concentrations Equalled or Exceeded by 20%, 50% and
80% of the Values for'5, 10, and 14 foot Depths in the
Garaeland's Trench Lysimeter (SGL). 351
156 Phosphorus Concentrations Equalled or Exceeded by 20%,
50% and 80%, of the Values for 6-, 10.4-, 17.5- and
20.3-foot Lysimeters (SLG-1) 351
157 ABS Concentrations Equalled or Exceeded by 20%, 50% and
80% of the Values for 6-, 10.4-, 17.5- and 20.3-foot
Lysimeters (SLG-1) 354
158 Chloride Concentrations Equalled or Exceeded by 20%, 50%
and 80% of the Values for 6-, 10.4-, 17.5-, and 20.3-
foot Lysimeters (SLG-1) 357
159 Nitrate-Nitrogen Concentrations Equalled or Exceeded by
20%, 50% and 80% of the Values for 6-, 10.4-, 17.5-,
and 20.3-foot Lysimeters (SLG-1) 357
160 Nitrate-Nitrogen Concentrations Equalled or Exceeded by
20%, 50% and 80% of the Values for a Suction Lysimeter,
SLK-1, in a Cropland!/ Area at the Gamelands Which
Received Two Inches of Effluent Per Week, Year-Round,
Since July, 1965 362
161 Estimates of Recharge to the Groundwater Reservoir on Each
Acre Receiving Two Inches of Effluent Per Week 366
162 Selected Values for Coefficients of Transmissivity and
Storage Obtained from Pumping Tests Conducted in the
University Well Field (Madified from S. H. Siddiqui,
1969) (101) 370
163 Relation Between Aquifer Hydraulic Properties and Water
Table Buildup for Two Oliversity Water Supply Wells 374
164 Effluent Storage Needs 405
165 Costs of a Land Disposal System for Treated Municipal
Wastewater (1967 dollars) 408
XXVlll
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SECTION I
CONCLUSIONS
1. Application of secondary treated municipal wastewater to cropland
at levels of one or two inches at weekly intervals results in a
guaranteed economic level of crop yield while at the same tine re-
charging 60 to 1001 of the applied wastewater as potable water on a
well-drained, silt loam or clay loam soil.
2. Application of secondary treated municipal wastewater to forest
areas at a level of one inch at weekly intervals on a well-drained
silt loam or clay loam soil results in improved diameter growth of
the trees and recharge of 60 to 100% of the applied wastewater as
potable water.
3. Application of secondary treated municipal wastewater to forest
• areas at a level of two inches at weekly intervals during the growing
season varied in its effects depending on soil and vegetative cover
type. On the Hublersburg silt loam or clay loam soil red pine growth
was adversely affected but white spruce height and diameter growth
was more than doubled. On the red pine area, with no ground vegetation,
nitrate-nitrogen concentration in the soil water at a depth of four
feet exceeded the U.S.P.H.S. recommended value for potable water but
on the white spruce area, with a lush ground vegetation, nitrate-
nitrogen remained well below the U.S.P.H.S. value of 10 mg WyN per
liter. On the other hand, year-round irrigation on a well-drained
MDrrison sandy loam soil, with mixed hardwood cover, diameter growth
was doubled but nitrate-nitrogen levels at a depth of four feet
greatly exceeded 10 mg N03-N per liter.
4. After four years, application of four inches of wastewater per
week as a split application of two inches each on Manday and Thursday
on a silt loam soil with a mature hardwood cover resulted in nitrate
concentrations in the soil water which were well below the U.S.P.H.S.
drinking water limit and phosphorus concentrations which were no
greater than on the control.
5. Crop removal contributes substantially to renovation of the waste-
water by removing the equivalent of 20 to 80% of the applied phosphorus
and 40 to over 100% of the applied nitrogen. Absolute amounts of P
removed ranged from 10 to 59 Ib/acre and that of nitrogen ranged from
36 to 356 Ib/acre.
6. Phosphorus not used by the crop over a 7-year period has been
retained in the upper foot of the Hublersburg clay loam soil and in
the upper two feet of the Morrison sandy loam soil. Phosphorus con-
centration in the soil water at the four foot depth has remained the
same on both the wastewater-treated and control areas.
-------
7. Chemical water quality changes in deep (160 to 300 feet) monitoring
wells, on-site, have been non-significant at the cropland and frj65*
areas with the Hublersburg soils but significant increases in nitrate
and chloride occurred in one well on the forested Morrison sandy loam
area. The concentrations, however, have remained well below the v.b.
P.H.S. drinking water limits for these constituents and all other
recommended drinking water limits.
8. Chemical composition of harvested crops treated with wastewater
were well within the normal range of such crops as reported p agrono-
mic literature. Effluent treated hay crops were generally higher in
content of phosphorus, nitrogen, potassium, magnesium, chloride, and
sodium than fertilized but unirrigated crops. The same was true for
the corn crops except for nitrogen, in which case the effluent treat-
ment effect was about equally positive and negative.
9. The principal soil chemical changes induced in the Hublersburg
soil by wastewater treatment were: 1. a substantial increase in Bray
extractable phosphorus in the upper foot of soil; 2. a large relative
increase but small absolute increase in exchangeable sodium in at least
the upper five feet of soil; 3. a substantial increase in exchangeable
magnesium to a depth ojf five feet; 4. a significant but small absolute
increase in exchangeable manganese in the third, fourth and fifth foot;
and 5. a significant and large increase in IffyNOj-extractable chloride
in at least the upper five feet of soil.
10. Boron concentration in the wastewater and transit through the soil
does not constitute any immediate or future hazard to crop or forest
growth, or to the groundwater.
11. Hydraulic loads of two inches of wastewater at weekly intervals
year-round, caused no surface runoff on the forested M>rrison sandy
loam site or on the forested or corn rotation Hublersburg clay loam
soil site irrigated from April to November, The same hydraulic load
on a grassed Hublersburg clay loam soil resulted in up to 100% surface
runoff when the soil was frozen and covered with ice.
12. On sloping areas with slowly permeable subsoils hydraulic loads
of two inches at weekly intervals can result in a perched water table,
dbwnslope interflow and seepage to the surface at breaks in the slope.
Phosphorus and nitrogen content of the water is substantially decreased
in such flows.
13. Programming the hydraulic load of one or two inches at weekly
intervals maintained an aerobic condition in the upper root zone of
the Hublersburg clay loam soil on the corn rotation area. The transient
perched water table on the 2-inch reed canarygrass area is probably
contributing substantially to the nitrate removal capacity of this area
by inducing denitrification.
-------
14. Irrigation equipment available on the commercial market is
adequate for year round operation under central Pennsylvania weather
conditions in either cropland or forested areas.
15. Estimated annual costs for a spray irrigation system containing:
a pumping station, a storage lagoon with a capacity equal to forty-
times the average daily flow, land costs of $140 per acre, a two-inch
per week wastewater load, a one-mile force main with a 200 foot eleva-
tion lift, a solid set aluminum piping irrigation system with 98 foot
lateral spacing and 70-foot sprinkler spacing with 3-foot risers,
labor and power costs, amortization of capital costs over a 20-year
period at 6% interest, engineering and contingencies at 101 of capital
costs were: 1MGD - $46,570, 5MGD - $146,800, 10MGD - $263,060.
16. Estimated annual cost per equivalent dwelling unit (3-5 persons
at 100 gallons per capita per day) with the parameters cited in item
15 range from $13.00 per year for a 1MGD system to $8.00 per year for
a 10MGD system.
-------
SECTION II
RECOMMENDATIONS
1. These studies were carried on at well-drained soil sites. Similar
studies should be made on moderately well to poorly drained soils to
evaluate their inherently greater denitrification potential.
2. The feasibility of wastewater treatment by the land has been
established. Studies should be conducted on whether the same pipeline
and irrigation system can be utilized for land treatment of the sewage
plant digested sludge, thereby decreasing the total sewage treatment
cost. Studies initiated in 1971 look very promising.
3. The effects of wastewater application on other segments of the
total ecologic system on the landscape need to be investigated notably
the game animals, songbirds, insects, etc. With the University about
to install a 4MGD land treatment system in 1974 approximately 500
acres would become available for such studies.
4. Further studies need to be made on how the hydraulic loading might
be varied to stimulate greater removal of nitrogen by denitrification
within the soil profile.
5. Further investigations would be desirable on the utility of
treated municipal wastewater and/or sludge on sites with high value
forest products such as Christinas trees, ornamentals, nursery seed-
lings and high population density - three to five year rotation pulpwood.
6. An in depth study is needed on the economic evaluation of a waste-
water recycling site in terms of the total water resources of an area,
particularly in the development of a -plan for the management of the
•water resources of a municipality.
7. Human health aspects of a spray irrigation wastewater recycling
system need to be evaluated with respect to:
a. The dispersion of pathogens, especially viruses in aerosols
derived from spray irrigation.
b. The survival of enteric pathogens in the soil and on vegetation
and the probability of hazard to livestock and humans.
8. Heavy metal data obtained in this study was confined to assays for
copper and zinc in a few forest foliage samples. Although the heavy
metal concentrations in the wastewater have been low further studies
would be desirable on the fate of these metals in the soil and their
probable future effect on plant growth and food chain aspects and on
soil micro- and macro-flora and fauna.
-------
9. Although two satellite studies have been completed on the effects
of wastewater application on wood quality, additional studies with
other species are needed.
10. In the present study there have been indications of changes in
dominance of certain species in the understory of wastewater treated
hardwood stands. The long term implications of this for the ecosystem
stability of a forest plant community and forest tree reproduction
should be studied.
-------
SECTION III
INTRODUCTION
Dilution of wastewater in streams and lakes is no longer satisfactory
in part because many wastes alter the balance of life in the stream
or lake and in part because the abundance of nutrients in the wastes
causes excessive growth of aquatic weeds which detracts from the
aesthetic and recreational value of the body of water.
The need to find methods for disposal of wastes other than by emptying
them into streams, lakes, and oceans, the desire to conserve the nutri-
ents by growing useful vegetation rather than aquatic weeds and the
urgency of replenishing the groundwater supply by recharge of the
renovated waste water led to a consideration of the feasibility of a
terrestrial means of disposal.
The problem in State College, Pennsylvania, was the degradation of
Spring Creek which resulted from the enrichment of the stream by the
nutrients in the effluent from the sewage treatment plant. As a
result, portions of the stream became choked with vegetation. For
this reason a study was initiated at The Pennsylvania State Univer-
sity to determine: (1) the feasibility of the year-round disposal of
sewage effluent on land; (2) the degree of renovation of sewage efflu-
ent by means of biological chemical and mechanical processes in soils;
(3) the extent of conservation of water by returning it to the ground-
water supply; and (4) the effects of the application of effluent on
soils crops, trees, and wildlife. The attack on the problem was ini-
tiated by assembling an inter-disciplinary team of research personnel
including agricultural and civil engineers, agronomists, biochemists,
foresters, geologists, microbiologists, and zoologists. After defin-
ing the problem and reviewing alternative solutions, plans and proce-
dures were developed with the advice and counsel of representatives
of the Pennsylvania Department of Health. The plans called for
testing a system for spraying sewage effluent on croplands and forested
areas to establish a cycle of renovation (Fig, 1) which would use and
purify waste water and return most of it to the underground reservoir.
Preliminary studies of potential disposal sites indicated that areas
were available on University farm and forest land and contiguous state
game-lands. More intensive geological studies indicated that soil
mantle thickness, character of the bedrock, and depth to the permanent
water table were satisfactory. A monitoring network was established
within a 10-mile radius of the proposed project sites and consisted
of approximately 50 private and public wells, six springs and one
stream. Beginning in April 1962, for one year prior to application
of any effluent, water samples were collected from this network and
chemically and bacteriologically analyzed (Fig. 2).
-------
o
a>
ae
o
S +
y
/ / Treatment /n
r PUr.t S(->^ j
Ground Water
Reservoir
FIGURE 1. The Waste Water Renovation and Conservation Cycle
-------
On November 1, 1962, the Sanitary Water Board issued a permit to the
University authorizing the disposal of effluent by spray irrigation
on certain terrestrial sites under specified conditions. The pumping
plant, pipeline, and irrigation systems were designed and installed
and the first effluent applied by May 16, 1963 (Fig. 2).
The University financed the studies for the first three years through
State and Hatch funds. This continuing support was supplemented on
May 1, 1965, by a Water Supply and Pollution Control Demonstration
Project Grant (WPD 95-01-65) from the Public Health Service of the
U. S. Department of Health, Education and Welfare and subsequent
grants, WPD 95-02, 03 and 04 of successor agencies, FWPCA and FWQA,
U.S.D.I. and E.P.A., and an O.W.R.R.-U.S.D.I, matching grant.
Detailed descriptions of the geology, hydrology, vegetation, soils,
monitoring systems and preliminary results to 1965 were reported in
Penn State Studies No. 23 (1) and interim reports on various segments
of the study have been published as journal articles and conference
proceedings and have been the subject of approximately twenty graduate
theses. A listing of these publications is given in the Appendix.
Coordination of the project was under the direction of Dr. Michael A.
Farrell, Director of the Agricultural Experiment Station, until 1968
and subsequently under Dr. Louis T. Kardos, Environmental Scientist,
in the Institute for Research on Land and Water Resources.
The principal objectives of the project were:
1. To determine to what extent the biological complex of forest,
crops and soil is capable of preparing sewage effluent for
recharge and reuse.
2. To determine criteria for selecting non-aqueous sites for
safe disposal of sewage effluent.
3. To develop and apply to the data gathered under Objectives
1 and 2 a systems analysis procedure for the determination
of minimum net costs for land disposal systems in terms of
municipal sewer service charges.
-------
St li
550
37
* Agronomy and
i Forestry Area
F-3
.,.*•". 'cu Pumping Stationi
University ->„,' K (
Sewage
Plant
State College, Pennsylvania
Explanation
Irrigation Sites
_____ 6" Diameter Effluent
Trunk Line
Creek
Bellefonte Central
Railroad
Improved Road
Gravel Road
• 8 Private Water Well
• UN-14 University Water
Supply Well
On Site Deep
• F-l Monitoring Wells
of Private or Public Spring
• St 1 Surface Water
Sampling Station
Figure 2. Location of Waste Water Renovation and Conservation Eacilities and Network of
Mbnitoring Wells and Springs.
-------
SECTION IV
SITE DESCRIPTION AND EXPERIMENTAL PROCEDURES
SEWAGE TREATMENT PLANT AND WASTEWATER QUALITY
The effluent applied at the irrigation sites is wastewater from The
Pennsylvania State University and the Borough of State College, Pa.,
which has been completely treated in a wastewater treatment plant
owned and operated by the University. The plant serves a total of
13,000 permanent residents and another 20,000 students at the
University most of the time. It also serves the entire University
with its diversity of wastes.
The present wastewater treatment facility shown in Figure 3 is
actually two parallel, two-stage treatment plants each having a
design capacity of approximately two million gallons per day (mgd).
One plant treats University sewage and excess flow from the half of
the plant treating Borough wastewater. It contains primary treatment
units consisting of a barminutor, pre-aeration (1.90 hours, detention
times based on average flow), and primary settling (3.63 hours). The
first stage of secondary treatment is provided by two high rate (76-
foot diameter by 6-foot stone depth) trickling filters while the
second stage consists of a modified activated-sludge process (2.25
hours) followed by final settling tanks (2.81 hours).
The parallel plant treats a portion of the Borough sewage. The
primary treatment units in this plant are a barminutor and a grit
chamber. Secondary treatment is a two-stage, modified activated-
sludge process carried out in two oxidators of the Halmur type
operating in series. Each oxidator has a central circular aeration
chamber (1.25 hours) surrounded by a concentric settling tank (2.86
hours). Excess activated sludge is concentrated in a flotation
thickener before it is digested. A single, separate sludge-digestion
facility serves both plants. It contains two heated sludge digesters,
the primary unit having a floating cover and Perth gas recirculation
system and the secondary unit a floating gas holder. Each unit is
50 feet in diameter with an 18-foot side-water depth and 4-foot-deep
conical bottom. Supernatant liquor can be aerated and returned to
the influent end of the plant treating University sewage but usually
it and the digested sludge are pumped into a tank truck and distrib-
uted on hay and pastureland.
Disinfection of the combined final effluent from both plants is
accomplished in two chlorine contact tanks with a contact time of
14.2 minutes at a maximum design flow of 15 mgd. Present contact time
averages about 35 minutes. Chlorination is controlled to give a re-
sidual chlorine of at least 0.5 mg/1. The effluent from these tanks
may be discharged into a small pond known as the Duck Pond or into a
11
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r—Gr^aj----
FROM
BORO
BARMINUTOR '
n J
FROM
BORO
LEGEND
— RAW WASTE OR SLUDGE
— EFFLUENT
f— SUPER
FINAL <
EFFLUENT
BARMINUTOR
PRIMARY
SETTLING
TANKS
jFLOTATION
I SLUDGE '
'THICKENER '
' BORO \
.^SECONDARY!
^AERATION /
\
HIGH RATE
TRICKLING
FILTER
HIGH RATE
TRICKLING
FILTER
PUMP
HOUSE
FINAL
SETTLING
TANKS
FINAL
AERATION
TANKS
CHLORINE
CONTACT
TANK
FROM
UNIVERSITY
IGESTED
SLUDGE
Figure 3. Flow Diagram Schematic of University Waste Water Treatment Plant.
-------
24-inch pipeline that by-passes the pond. Although this effluent does
not have the quality of drinking water, it is relatively clear and
odorless and would not cause any physical nuisances. A typical ex-
ample of the physical and chemical composition of the effluent is
shown in Table 1.
The quality of the wastewater applied to the various experimental
areas is given in greater detail in later sections. The fertilizer
equivalent value of the wastewater applied to the Agronomic Area is
given in Table 2. The average cost to a farmer in purchasing the
major fertilizer nutrients applied per acre annually with the two-
inch per week additions from .Apr to Nov would be about $50. Or
expressed in other terms each inch of wastewater applied per acre has
a fertilizer value worth approximately $.85. This represents a sub-
stantial contribution to any spray disposal area which would be used
for food, feed or fiber production.
Microbiological assays of the wastewater as it arrived at the disposal
site (2) showed an average total coliform density of 578 per 100 ml
in 26 samples over the period 7/8/65 - 4/22/66. This value is below
the reconmended limits for recreation use other than primary contact.
If the fecal coliforms were to constitute less than 40% of the total
coliforms (a highly probable case), the wastewater would also meet
the recommended limits for primary contact recreation water.
In a virus isolation study conducted by Dr* Ernest H. Ludwig, Prof.
of Microbiology, 30 "sewer swab" samples of the chlorinated waste-
water were obtained during a nine week period, Aug 16 - Oct 17, 1967.
One half of the samples were obtained at the outflow of the chlorine
detention tank at the sewage treatment plant. The other 15 samples
were obtained from a four-inch irrigation main 2% miles from the
sewage plant at the Agronomy Area. Water from the supply line was
allowed to flow through a 240 gallon tank at a rate of 2.0 gallons per
minute. Sampling at each location was accomplished by suspending a
4 inch x 4 inch cotton gauze "sewer swab" in the flow for 3 or 4 days.
In this manner sampling of the wastewater was continuous for the nine-
week period. Each pair of samples from the two sampling positions had
an equal exposure period. Cultures of rhesus monkey kidney cells and
hunan amnion cells were each innoculated in duplicate with isolates
from the "sewer swabs" and all samples were passed to a second set of
fresh cell cultures at least one time. Additional passages were made
when deemed necessary.
With these procedures no virus isolated from any of the samples from
the irrigation line at the field site. One agent isolated from the
sample representing the period, Sept 22-25, at the outflow from the
sewage treatment plant. These data indicate that the probability of
viral contamination in a reasonably sanitized wastewater is very small
13
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Table 1. Composition of Sewage Effluent
Concentration - mg/1
Substance Aug, '69 - Aug, '70a 1968-70b
Turbidity (Jackson Units)
Residue
Total
Fixed
Suspended Residue
Total
Fixed
Biochemical Oxygen Demand (BOD)
Alkalinity as CaCo?
Sulfate as SC>4
Aluminum
Organic - N
Ammonia - N
Nitrate - N
Apparent ABS (MBAS)
Orthophosphate as P
Potassium
Calcium
Magnesium
Sodium
Chloride
12
360
220
25
3
15
140
40
0.15
4.9
11.0
5.1
0.5
5.3
15.0
27.0
13.5
41.6
48.3
a Analyzed in Sanitary Engineering Lab.
Analyzed in Agronomy Department Lab. Average of 104 weekly composite
samples obtained during irrigation of Agronomy Areas.
14
-------
Table 2. Composition of Applied Effluent Expressed as a Fertilizer
Equivalent Formula, N:P:K, at a Rate of 1000 Ib per Acre
Fertilizer Equivalent Formula (N-P-K)
Year 1 Inch per Week 2 Inches per Week
1963
1964
1965
1966
1967
1968
1969
7 -
14 -
6 -
10 -
O *"
9 -
9 -
5 -
6 -
4 -
4 -
3 -
2 -
2 -
9
12
13
15
10
8
5
14
25
11
18
11
20
16
- 10 -
- 13 -
- 9 -
- 8 -
- 8 -
- 6 -
- 5 -
18
23
27
28
21
15
10
and of no concern, particularly in as much as the soil filtration
which would occur provides an additional very effective safety factor.
PIMPING PLANT AND WASTEWATER DISTRIBUTION SYSTEM
The pumping plant which supplies the effluent to the irrigation appli-
cation sites is located on the 24-inch pipeline that by-passes the
Duck Pond (Figure 2). A sump which functions as a pump pit was
installed at the by-pass line. Effluent in excess of that required
by the pumps is permitted to continue out of the sump via the 24-inch
line to Thompson Run, the normal disposal channel.
A pump house was constructed over the 10 x 10 x 8-foot sump. This
house contains two pumping plants which are alternated manually, one
serving as a standby. Each pumping plant includes a vertical centrif-
ugal pump, designed for an output of 350 gallons per minute (gpm) at
520 feet (226 pounds per square inch) total head, and a 60 horsepower,
3-phase electric motor. The pump house also contains an in-line meter,
which measures the amount of effluent pumped, and a pressure-recording
instrument equipped with high and low pressure automatic signaling
devices to indicate possible failures in the distribution or irriga-
tion systems.
Leaving the pump house, a 6-inch steel pipe runs under Thompson Run
and beneath a major highway (Pennsylvania Highway 26, Benner Pike).
Beyond this, a 6-inch asbestos-cement line carries the effluent
generally in a northwest direction. At a distance of two miles, the
line divides: one 6-inch branch going a half-mile to the Agronomy and
Forestry Areas, the other 6-inch branch going two additional miles to
the Gamelands Area. All main lines are buried at least 18 inches.
Since this depth is not adequate to prevent freezing, the effluent
must be pumped continuously during cold weather. Appropriate vents
15
-------
and drains permit air removal and effluent drainage from the line when
necessary.
The first branch line terminates at the Agronomy and Forestry Areas
approximately two and one-half miles from and 175 feet higher than the
pumping plant; the second branch line terminates in the Gamelands Area
approximately four miles from and 280 feet higher than the pumping
plant. The pump supplies approximately 350 gpm at 70 psi to the
Agronomy and Forestry Areas or about 300 gpm at 45 psi to the high
point in the Gamelands Area. The rate and pressure desired are regu-
lated in each area by branch line valves.
IRRIGATION APPLICATION SYSTEMS
All pipe beyond the buried distribution system is above 'ground and
comprises the irrigation application systems. These surface systems
are composed of 4- and 5-inch aluminum main lines and 2- and 3-inch
aluminum lateral lines, which distribute the effluent to regularly-
spaced sprinklers on 1-inch diameter risers. The systems were design-
ed to distribute 350 gpm or 500,000 gallons per day.
The typical irrigation application systems most frequently used during
the first five years of operation are described in the report, Penn
State Studies No. 23 (1). These systems ordinarily applied effluent
to 3-acre areas at the rate of one-quarter inch per hour. For an
application level of two inches per week, valve changes every 8 hours
were required. One valve change each day occurred at midnight, which
for a manually operated system was not convenient. Thus, to ease
labor arrangements, to irrigate at a lower rate of application, and
in some cases to permit the use of smaller lateral lines, the irriga-
tion system was modified at some sites to allow a 12-hour period of
application.
By appropriate use of specific sprinklers, spacing of the sprinklers
along the laterals, spacing of the laterals, and adjustment of
pressure at each lateral, application rates of one-sixth or of one-
quarter inch per hour were provided at individual locations. For an
application level of two inches per week only three acres need to be
irrigated each 8-hour period or four and one-half acres each 12-hour
period to use 0.5 mgd continuously. Each arrangement irrigates nine
acres each day and thus, the system covers 63 acres in a week. The
three-acre or four and one-half acre plots can be subdivided further
to permit use of smaller diameter irrigation lines or to provide
better hydrologic conditions. Most of the areas received two inches
of effluent per week; however, various small experimental areas
received one, four, or six inches per week (Table 3).
A solid-set irrigation system was used in all areas. That is, main
and lateral lines were not moved from position to position, as is
16
-------
Table 3. Monitored Irrigation Areas and Application System Parameters, 1963-1969
Location
and Area
Soil Series
Agronomy (A)
Hublersburg
Clay Loam
Forestry (F)
Hublersburg
Clay Loam
Game lands (G)
Morrison
Sandy Loam
No.
1
2
3
1
2
3
4
5
1
2
3
4
Vegetative
Cover
Farm Crops
Farm Crops
Reed Canarygrass
Red Pine
Red Pine
Red Pine
Hardwoods
Old Field
Hardwoods
Hardwoods
Hardwoods
Farm Crops
Initial
Irrigation Irrigation
Date
May,
May,
July,
June,
June,
July,
June,
June,
Oct,
Oct,
Nov,
Nov,
1963
1963
1964
1963
1963
1964
, 1963
1963
1964
1964
1965
1965
Period
Apr-Oct
Apr-Oct
Jan-Dec „
Apr-Nov
Apr-Nov
Apr-Nov
Apr-Nov
Apr-Nov
Nov-Mar
Nov-Mar
Jan- Dec
Jan -Dec
Sprinkler
Weekly Sprinkler!/ Spacing
Load Discharge Feet t
Inches
1
2
2
1
2
2
1
2
2l/
4V
2
2
gpm AxB£/
16
16
16
6
6
6
8
8
6
6
6
16
.6
.6
.6
.2l/
.2^1
.2
.3
.3
.2
.2
.2
.6
80x80
80x80
80x80
"jjp* ,
60x40l/
60x40
80x40
80x40
60x40
60x40
60x40
80x80
Area
Acres
4.
4.
16.
1.
1.
13.
0.
0.
11.
3.
3.
2.
4
4
0
0
0
5
5
5
0
0
0
0
— Application rate was % inch per hour for all systems.
2/
A - distance between sprinklers in line; B = distance between lateral lines.
— During 1963-67 sprinkler discharge was 8.3 gpm at a spacing of 80x40 ft above the canopy on
risers which were 42 ft long.
4/
Weekly load was 6.0 inches in winter of '64-'65 and was followed by spring, summer, and fall
irrigation, in 1965 only, at indicated loads. In subsequent years, through 1969, irrigation
was only in Nov-Mar and both areas G-l and G-2 received 4 inches weekly.
-------
frequently done in agricultural crop irrigation. This permanent
arrangement is preferred since it is difficult to move pipe among the
trees; it is nearly impossible to move pipe when it is covered with
ice; and the laterals used during winter need to be on a continuous
grade to provide rapid draining during freezing weather.
Certain .Agronomy and Forestry Areas were irrigated only during the
period, mid-April through mid-November, (Table 3). Sprinkler heads
in the Agronomy Farm Crop Areas were staggered, with a distance of 80
feet between sprinklers along the laterals and 80 feet between later-
als. Each sprinkler emitted 16.6 gpm. Since this amount, on the
average, was applied to each 80 x 80-foot area, the application rate
wsts one-quarter inch per hour. A portion of the Reed Canarygrass Area
had sprinklers placed on 80 x 100-foot spacings and applied the efflu-
ent at one-sixth inch per hour. The wider spacing is preferred since
it permits lower original system costs and more convenient farming
operations.
Table 3 also indicates the various spacings and application rates for
the irrigation systems in wooded areas. Some of the variation was due
to physical area restraints or for providing flexibility in the total
system. On the basis of operational experience and of data presented
in the irrigation systems operation section, the preferable spacing
for wooded areas is 60 x 60 feet. This seems to give the best
compromise between uniformity of distribution and cost of original
equipment.
SITE CHARACTERISTICS
Physiography. The research area is located at the western edge of
the Ridge and Valley section of the Folded Appalachian province.
Youthful valleys of Spring Creek, Big Hollow, Buffalo Run and their
dry tributaries are incised from 50 to 300 feet below rolling upland
surfaces. Spring Creek is a rather small stream with a flow ranging
from 10 .to 990 cubic feet per second as it leaves the region. The
stream drains the limestone Nittany Valley, and is fed by springs
with flows up to 1.0 million gallons a day. The valleys except for
Spring Creek are underdrained by solution channels developed near the
top of several hundred to several thousand feet of dolomite and lime-
stone bedrock. The water table underlies the valley bottoms from 10
to 75 feet below the ground surface. In adjacent uplands and along
interfluves, the unconfined water table ranges from 50 to 325 feet
below the surface. Big Hollow is a dry karst valley except for a few
days of the year when runoff occurs along short segments of the valley.
Buffalo Run Valley to the northwest of the disposal site has an in-
fluent stream which carries water during the spring and is dry the
remainder of the year. Outcrops are present but sparse along the
walls of the valleys. Uplands normally lack integrated drainage
because differential weathering has produced a hummocky topography
18
-------
which retains surface water temporarily in depressions. Organic
matter has accumulated in some depressions, helping to seal the
bottoms and creating perched surface water ponds under normal rain-
fall conditions. IJpland surfaces are covered by 5 to 161 feet of
unconsolidated residues consisting of clay, silt and sand.
The range in thickness and composition of the weathered soil mantle,
the character and thickness of bedrock strata, and the depth to the
groundwater table were established through a drilling program initi-
ated in May 1962.
Bedrock. The land on and adjacent to the research sites is underlain
by a thick sequence of limestone and dolomite with inter-connected
solution openings and cavities. Stratigraphic and structural studies
(3, 4) were carried out to determine whether cavernous intervals are
controlled by rock type, whether individual bedrock units serve as
confining beds to groundwater movement, and whether solution zones
are open or debris filled.
The rocks in the region of the effluent disposal sites were found to
be structurally deformed into at least two anticlines (one of which
is overturned) and a syncline. These deformities have more than 500
feet of closure. The northwestern border of the area is cut by
several major thrust faults and by numerous minor normal and cross
faults that extend into the area immediately adjacent to the irriga-
tion sites. Most of the faults facilitated extensive weathering and
are associated with zones of increased thickness of soil mantle.
They also provide avenues for water movement.
Permeability of the faulted rock is 40 to 100 times greater than that
of the adjacent sound bedrock. The Burmingham Thrust Fault, exposed
along the northwestern margin of the study area, has a low angle dip
to the southeast and completely underlies both disposal sites. At
least two thrust faults are exposed in the outcrop area of the Burming-
ham Thrust. These undoubtedly converge at depth and give rise to a
single, low-angle thrust fault. A significant volume of groundwater
moves into this fault zone and flows northeastward toward Spring
Creek.
Fracture traces--surf ace indicators of underlying, nearly-vertical
zones of fracture concentrations--were found to be useful prospecting
guides in locating zones of increased weathering, solution and perme-
ability (5). Maximum solution development was found at or near the
center of fracture traces. The permeability of fracture rock is 10
to 100 times that of adjacent unfractured rock. Fracture traces also
delineate zones of more intense weathering, outlining regions where
the soil mantle is 20 to 100 feet thicker than normal. Deep monitor-
ing wells were located on these traces since they concentrate ground-
water movement.
19
-------
The rocks immediately underlying the disposal area comprise the
Gatesburg Formation which has been subdivided in descending order
into the dolomitic Mines Member, interbedded sandstones and dolomites
of the Upper Sandy Member, dolomites of the Ore Hill Member, and
interbedded sandstones and dolomites of the Lower Sandy Member.
Stratigraphic studies revealed that where sandstones occurred, cavi-
ties were localized and the mantle was thicker. Solution zones are
concentrated along sandy-dolomite and dolomite-sands tone beds. These
beds have a higher primary porosity and less total cement than adja-
cent, more dense dolomite beds and, hence, weathered more readily.
Solution cavities were found to be more abundant in the highly-
weathered upper 100 feet of bedrock.
In general, bedrock cavities were found to be of two types: a) solu-
tion cavities in dolomitic bedrock; and b) loose-to-friable zones
and/or cavities in sandy dolomite to dolomitic sandstone beds. The
first type is principally joint or fracture controlled. The second
type occurs in sandstone beds from which the cement has been dissolved
and is controlled by joints and fractures and by bedrock lithology.
Cavities are generally five to twenty feet thick in the upper 100
feet of bedrock and less than one to three feet thick at greater
depths. Shallow bedrock cavities connected to the weathered mantle
appear to be filled with debris from the mantle. Their presence is
commonly indicated by shallow depressions at the surface.
Extensive cavities were not encountered; rather, cavities are local-
ized where joints, faults or fracture zones intersected bedding
planes or porous strata. Groundwater is believed to flow from be-
neath the irrigation sites along a system of interconnected open
joints, bedding planes, and fracture systems.
Three types of cavity-fill materials were distinguished: a) unsorted
mixtures of sand, clay, and blocks of bedrock; b) sandstone rubble
and/or sand containing varying amounts of silt and clay, and; c) clean,
well-sorted silt and sand. The majority of bedrock cavities from
which split-spoon samples were collected are above the water table
and are of the first type. The fill was derived from slumping of the
overlying weathered mantle. The second type of cavity-fill material
is present in sandstone beds from which the cementing agents have been
removed by weathering. The third type, recorded as "running sand"
by drillers, lies below the water table in joints and in bedding-
plane and solution openings. Most of the fill material serves as an
additional adsorption and filtering medium for percolating water,
Weathered Mantle. The drilling program begun early in 1962 helped
establish the range of weathering conditions which might be found at
the potential sites. Test holes were drilled in uplands, adjacent to
valley walls, along valley bottoms, and on topographic highs and lows.
20
-------
Split spoon samples were obtained from the weathered mantle at one-
to five-foot intervals and from bedrock cavities which were more than
one to two feet thick.
A shallow seismic program was also conducted at the Agronomy and
Forestry Areas to determine the soil thickness and configuration of
bedrock suface. Measurements were made at 50-foot intervals along
straight lines 520 feet long. A second test drilling program was
carried out in the spring of 1963 to outline spots of thin soil cover
within these areas and to confirm seismic interpretations.
The weathered mantle of the research areas was found to be composed
of randomly occurring thin-to-thick beds of mixtures of clay, silt
and sand which have accumulated as relatively insoluble residue from
carbonate bedrock. Many of these beds have been truncated by surface
erosion or draped into solution depressions within the bedrock sur-
face and preserved against erosion. Chemically-resistant pebbles,
cobbles and boulders of chert, nodular and bedded oolitic chert,
quartzite, hematite-cemented sandstone, and fault breccia are distri-
buted throughout the mantle.
The thickness of the weathered soil mantle was found to be greater
above zones of increased solution. Dish-like depressions which con-
centrate water occur above these zones. Perched water tables persist
for varying periods in more permeable beds below some of these de-
pressions. At other positions above zones of increased solution,
sink-holes have developed in which there is virtually no soil to
retard the flow of water. Such depressions, if irrigated, would pose
a hazard to the project since they could allow applied effluent to
recharge directly to the groundwater.
Soils. Soils derived from the Upper and Lower Sandy Members of the
Gatesburg Formation at the Gamelands Area are quite permeable and
contain large amounts of sand. The Morrison sandy-loam and Gatesburg
loamy-sand are two representative soil types derived from this rock
and occupy most of the forested portions of the Gamelands Area. The
cation and anion exchange capacities of these sandy-loam soils are
less than that of the Hagerstown and Hublersburg silt loam and silty-
clay loam soils derived from the Mines and Ore Hill Members of the
Gatesburg Formation which are present in the cultivated portions of
the Gamelands Area and cover most of the upland surface of the
Agronomy and Forestry Areas. Detailed description of modal soil
profiles of these soil types are given in (1).
Along segments of the dry bottoms of Big Hollow valley and its tribu-
taries, weathering and erosion have extended through the Mines and
Ore Hill Members into the top of the Upper and Lower Sandy Members of
the Gatesburg Formation, resulting in isolated patches of Morrison or
Gatesburg soils along the valley walls.
21
-------
Groundwater. The orientation of most of the valleys tributary to Big
Hollow and Buffalo Run is controlled by fracture traces, formational
contacts, and fault zones. The position of Big Hollow is related to
differential weathering of the eastward-dipping Mines Dolomite and the
more soluble, overlying Stonehenge Limestone. The same condition that
helped localize stream erosion helps capture surface water and convey
it to solution zones beneath the valley. This surface runoff dis-
solves the underlying bedrock to produce open sink holes, which makes
the valleys unsuitable for irrigation sites.
The water table in this region has relatively low relief and a nearly
uniform gradient. It underlies uplands at depths of 100 to 350 feet.
Thus, there is no danger of excessive surface waterlogging at the
irrigation site due to a rising water table. Minor waterlogging may
result from rising perched water-table levels.
Best estimates for the coefficient of transmissibility range from
100,000 to 150,000 gallons per day per foot (gpd/ft), as calculated
from data obtained from wells located on fracture traces, and 1,000
to 4,000 gpd/f t in blocks of carbonate rock bounded by zones of
fracture. These relatively high transmissibility values for solution
zones combined with the relatively flat water table indicate that
groundwater may move freely from the irrigation sites and other areas
of groundwater recharge.
Prolonged drought combined with continued natural discharge and pump-
age from wells in the area were undoubtedly responsible for water
table declines in 1962-65. A rainfall deficit of 26 inches was
recorded for this period by the Department of Meteorology at The
Pennsylvania State University. At the same time, vast volumes of
groundwater were discharged from springs into Spring Creek to the
northeast. One of these springs has an approximate flow of 4,320,000
gallons per day. In addition, nearly two million gallons of ground-
water were pumped each day from University wells. The pumping cone
of depression around the University well field deepened during this
dry period and expanded to divert more groundwater from the Agronomy
and Forestry Areas. A groundwater divide at the Gamelands Area in
1962, the remnants of which are shown in Figure 4, completely dissi-
pated and was replaced in 1965 by a groundwater trough (Fig 5) which
marks a major subsurface drainage way. The unconfined water table in
that area declined more than 60 feet in three years.
The presence of groundwater mounds beneath some topographic highs in
1962 prior to the drought, indicates that the uplands are recharge
sites and that valley bottoms localize groundwater drains. For short
periods of high runoff, localized and short-lived groundwater mounds
build up beneath the valleys where normally groundwater troughs are
located. The long-lived upland groundwater mound at the Agronomy and
Forestry Areas, although subdued from May 1962, was still observed in
April 1965. Groundwater flow was still away from this high in a
radial manner.
22
-------
04
23 •
G-3.
f-4
Sp-40"
A
S-2»
—iots-^-
Explanation
I Spray Irrigation Sites
Private Water Well
Monitoring Wells
Spring
University Water Supply Well
Elevation Based on Stream Stage
Scotia Wells
Contour Interval 25 feet
Direction of Ground Water Movement
1/2 0 1/2 1
Scale Miles
Figure 4. Water .Table Contour Elevations in March, 1963.
-------
Explanation
G-2
Monitoring Wells
UN-2* University Water Well
SP-2" Spring
8 • Private Water Well
|pj;ij| Spray Irrigation Sites
» Approximate Direction of Ground
Water Movement
— 92Sw Contour Interval 25 feet
Figure 5. Water Table Contour Elevations in April, 1965.
24
-------
Vegetation. The two major disposal areas chosen for the disposal of
effluent contained representative plots of forest, open fields, and
cultivated croplands which allowed .investigators to study the method
under different vegetative conditions.
The forested portion of the Agronomy and Forestry Areas (Fig 6)
includes approximately 70 acres of hardwoods and 90 acres of conif-
erous plantations, broken by open old-field areas.
The hardwoods at this site are primarily a mixture of white oak
(Quercus alba L.), black oak (Quercus velutina L.), red oak (Quercus
rubra L.), and scarlet oak (Quercus coccinea Muench), in association
witR a few hardwood species such as red maple (Acer rubrum L.),
mockernut hickory (Carya tomentosa, Nutt), black cherry (Prunus
serotina Ehrh), and flowering dogwood (Comus florida L.). The average
age of the dominant and co-dominant trees on the experimental plots
was 50 years. The average tree diameter was 14 inches and the average
height was 70 feet.
The coniferous plantations were established about 1939 on abandoned
agricultural land. The trees were planted at a spacing of eight by
eight feet. On the experimental plots of red pine (Pinus resinosa,
Art.), the average tree diameter was 6.8 inches, the average height
was 35 feet.
The cover in the open old-field areas was predominately a poverty
grass (Danthonia spicata, Beauv.)-goldenrod (Solidago spp.)-dewberry
(RubusJElagellaris, Willd.) plant community. One sparse stand of 9
year old white spruce (Picea glauca, Moench) was also in the experi-
mental area. Deer damage to the spruce by browsing has been extensive.
Height of the white spruce in 1963 ranged from 2 to 10 feet. The
average height of twenty paired sample trees used to measure response
to irrigation was 6.8 feet.
' Most of the adjacent Agronomy Area (approximately 70 acres) has been
managed by the University in a rotation consisting of corn, oats,
wheat, and one or more years of hay. A portion, however, has been
kept in a permanent hay cover (reed canarygrass). The rotation hay
crops were timothy and red clover or timothy and alfalfa.
The Gamelands Area contains approximately 200 acres of mixed hardwood
forest. The vegetation was composed largely of oaks, predominantly
white. The average diameter of 60 paired trees selected for measure-
ment was 10.4 inches with an average age of 40 years and an average
height of 50 feet. Ground cover was sparse.
MONITORING SYSTEMS
A diversified monitoring system was considered an essential part of
this feasibility study in order to learn the degree of renovation of
25
-------
•*•
UN-23
F-l
3-^:1-•
,-*• Red Pine Plantation
F-3
Explanation
Gravel Road
— — — Trail
• F-l Deep Monitoring Well
•&UN-14 University Water Supply Well
O Fm-16 Selected Shallow Sand-point Well
Sewage Effluent Trunk Line
Figure 6. Layout of the Agronomy and Forestry Areas.
26
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wastewater with depth of penetration in various soils within and below
the root zone and the quality of water being recharged to the ground-
water reservoir.
Both^an onsite soil-water and ground-water sampling network and an
offsite network of private and public wells and springs were part of
the monitoring system. A schematic diagram of the various types of
monitoring installations is shown in Figure 7.
N
Effluent Gauges. Throughfall rain gauges were used to determine the
amount of wastewater reaching the forest floor in the red pine plots
when sprinklers were above the tree canopy. Six of these gauges,
each 5 inches wide, 48 inches long, and 6 inches deep, were placed
at random in the 1-inch and 2-inch red pine treatment plots. The
gauges were installed with a slight gradient toward the drainage out-
let and were supported approximately 2.5 feet above the ground surface
on two wooden stakes. They were connected to 5-gallon collection cans
with rubber tubing.
Two small capacity rain gauges were placed beside each forest floor
pan and pan lysimeter. These were used to obtain an accurate measure-
ment of the amount of wastewater reaching the forest floor and
vegetative cover at the location of the percolate sampling instruments.
Forest Floor Pans. Cylindrical pans, each two inches in height with
an exposed surface area of 500 square inches, were filled with an
undisturbed sample of the forest floor (litter, fermentation and humus
layers). A gradient of approximately five per cent was maintained
toward the drain outlet. The filled pans were installed at ground
level in as natural a condition as possible. The percolate samples
were collected in a 3-gallon glass jug which was connected to each pan
by a rubber tubing. Two of these floor pans were filled and instal-
led in each treatment and control plot of the hardwood stands and red
pine plantation. The two pans installed within the control plot of
the red pine 2-inch application area served as controls for both red
pine treatment plots.
Pan Lysimeters. Pan lysimeters measuring 12 x 15 inches were construe-
ted of 16-gauge galvanized sheet metal with a drainage outlet of one-
half inch copper tubing. A pit was excavated deep enough to accommo-
date 10- and 20-gallon galvanized steel garbage cans and the pans were
inserted into the undisturbed face of the soil profile with a gradient
toward the outlet of approximately one inch per foot. The cans were
placed in the pit and the copper tube spouts were inserted into the
cans. After backfilling the pit around the cans, the forest floor was
replaced in its original position. A 4-quart plastic container was
placed in each can beneath the copper tubing to collect the percolate.
Samples were collected after each irrigation and each storm.
27
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Mixed Hardwoods
Red Pine
Abandoned Fields
Water Table-1 .
Bedrock
Dolomite and Sandstones
of Gatesburg Formation
A. Throughfall gauge
B. Lysimeters (In root zone at depth of 1 J inches to 4 feet).
C. Soil Moisture Access Tubes (To measure changes in
soil moisture— 8 to 20 feet deep).
D. Sand-point Wells (completed in the weathered
mantle at depths from 6 to 52 feet).
E. Deep Water-table Wells (Contain submergible or
piston pumps, 250 to 300 feet deep).
F. Trench with pan lysimeters at one foot intervals to
depths 6 and 16 feet.
G. Suction lysimeters, 6 inches to 26 feet in depth
H. Weather Station
Figure 7. Schematic Diagram of Various Types of Monitoring
Installations.
28
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The lysimeter pans were placed at depths of six and twelve inches in
the hardwood area receiving one inch of wastewater per week, in the
red pine area receiving two inches, and in the old field area receiv-
ing two inches per week. Similar pans were installed at three and
six inches in the red pine area receiving one inch of wastewater per
week.
Pan lysimeters were also installed along the walls of a six foot deep
trench in the Forestry area where effluent was applied at the rate of
4-inches per week during the growing season and in a 17-foot trench
in the Game lands where 4-inches per week was applied during the winter.
They were installed at depths of one-half, one, two, three, four, five,
and six feet in the 6-foot trench, and at one foot intervals from one
to sixteen feet in the 17 foot trench.
the trench walls were braced with timbers and siding treated with
liquid wood preservatives to prevent decay and to insure longer integ-
rity of supporting members. The seepage face was inclined 1 to 5
degrees from the vertical and sloped toward the direction where inter-
flow was expected. Metal pans were driven into the seepage face and
small voids above and below the pans which were created during in-
sertion were back-filled with native soil. Voids between the trench
face and protective siding were backfilled with soil and pea gravel
to allow soil water to flow freely to the pit floor (Fig 8 and 9).
Both pits were covered with a sloping roof and later the 17-foot
trench was provided with a wooden floor after the bottom began to
heave.
Parizek and Lane (6) pointed out the limitations and problems encoun-
tered with this method of sampling soil water. During the first
winter (1964-65), 6-inches of wastewater per week were applied to the
slope above the sampling pit in the Gamelands. After 12-inches of
water had been added, underflow became excessive and the pit was
flooded nearly to the roof by perched groundwater within a few hours.
To protect the sampling station, and avoid contaminating the soil
adjacent to the pit, a 90 foot deep floor drain was drilled and cased
to underlying dolomite. In subsequent years, when only four inches
or two inches were applied weekly, pit flooding did not occur.
The stratified nature of these residual soils, sloping character of
land, and large amounts of wastewater applied along the slope above
the trench lysimeter, helped to account for flooding problems encoun-
tered. A sump pump or floor drain would probably be required to
prevent flooding under similar circumstances particularly where more
than 2-inches of water a week in addition to rainfall are applied in
a humid region.
It was found that gravitational water samples could be obtained only
rarely from the trench lysimeters during the growing season when water
29
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2x12" Siding and
4x4" Timbers. All Wood
Treated with Preservative.
Gutter Drain
Pipe
Pan
Lysi meter-^
r 'Residual Soil
:" Stratified Silt,
. Clay, and Sand
~
Screen on
Floor Drain
2 Inch O.D.
Pipe
Dolomite
Bedrock
Figure 8. Schematic Diagram of Trench Lysimeter.
30
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•.-•2™i-f~ ->
. ^i - -W _ -*. v -- -
mmmmxEmm •-•&.*."---*+* „ -. ^« ---~~ _.*.. — .
Figure 9, Oblique View of Trench Lysimeter. Irrigation Lines in the Background Have a Two Percent
Grade to Provide Rapid Drainage to Prevent Freezing in the Winter.
-------
was not being applied in the immediate area. By 1968 all pan lysi-
meters were replaced by suction lysimeters in the forest areas
because there were several indications that the pans had rusted out.
Sand-Point Wells. Some exploratory test holes drilled to determine
the thickness and composition of the weathered soil mantle were used
as intermediate sampling points. Two-inch diameter steel pipes fitted
with 2 foot long sand-point screens were installed in these bore holes.
Approximately half of these wells were located beneath surface depres-
sions where the weathered soil mantle was draped into solution open-
ings within the underlying bedrock and where runoff and side hill
seepage might be excessive. These wells are completed in sand or silt
lenses within clay that contain intermittent perched groundwater at
depths of six to 60 feet as a result of subsurface flow. The 3-inch
diameter test holes were back-filled almost to the base of a selected
sandy-clay or silt bed. A 2-inch diameter, 2-foot long Johnson well-
screen was attached to the top of a three foot long reservoir pipe.
The lower reservoir pipe and overlying casing were embedded in a
.mixture of bentonite and native clay and washed silica sand was placed
opposite the screen. Each installation was flushed with well water
to remove clay in the vicinity of the screen. Water samples were
obtained by hand-bailing.
This method of sampling soil water was found to be of marginal value.
Perched groundwater did not form at all sampling locations. Abundant
volumes of water were available in some, in others, only occasional
samples could be obtained. Frequently, the sample volume was insuffi-
cient for the analyses to be performed.
Sediment entrained with the water posed analytical problems. The
screen slot size was sufficiently large to allow clay-sized material
to enter the sampling point. Also the mechanical bailing method
aggravated the problem by causing a surging action. A sand pack could
be designed to eliminate the sediment problem but a large diameter
hole, greater than 3-inches, would be required. Less surging would
result if a small capacity pump were left in place. An air-back
pressure method of pumping was tried but air freely entered the forma-
tion and escaped to surface outside the steel casing before water was
forced to surface on a consistent basis.
Despite these shortcomings, water samples were routinely collected
from a number of sand points at the Agronomy-Forestry Site.
Suction Lysimeters. Suction lysimeters, also referred to as vacuum
lysimeters, are used to obtain soil-water samples at shallow depths,
6 inches to 4 feet, and to depths of 26 feet or more at the research
sites. The devices used for shallow sampling are similar to that
described by Wagner (7), and were first installed by Kardos in 1964
in the Agronomy Area and later replaced the pan lysimeter in the
32
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forest areas. The method of installation is described in Edwards (8).
The suction lysimeters consist of a porous ceramic cup having an out-
side diameter of 1 7/8 inches and an overall length of 2 7/8 inches.
The cup is cemented to plastic tubing to provide an air and water-
tight seal. When the porous cup is moist it will hold a vacuum
equivalent to the vapour pressure of the water. The top of the
plastic pipe is plugged with a one-hole or two-hole rubber stopper.
Rigid tubing is inserted through the stopper and is fitted externally
with a short length of rubber tubing. With the one-hole stopper a
vacuum is applied to the assembly and maintained by closure with a
thumbscrew clamp applied to the rubber tube. To recover water samples,
the screw clamp is released, a small diameter rigid tube is inserted
through the rubber tubing and a vacuum is applied through a flask
which collects the water as it is withdrawn (Fig lOa). When using a
two-hole stopper, one of the rigid tubes, both of which are cut off
just below the stopper, is fitted with a length of tubing which
extends to the inside bottom of the ceramic cup. To evacuate the
chamber the connection is made to the rigid tube which ends just in-
side the stopper. To remove the sample from shallow positions suction
is applied to the tube which extends to the bottom of the chamber
after opening the tube which ends just inside the stopper.
f
This unit was modified by Parizek to allow soil-water samples to be
collected from depths greater than 20 feet. A detailed description
of this modified device is given by Parizek and Lane (6) and is shown
in Figure 10-b. Several dozen of these devices were installed at
depths of three to twenty-six feet below ground surface at the Game-
lands site. Many have been in use for six years or longer and are
still in good operating condition. More recently they have been shown
to be suitable for obtaining soil water samples from below a 60 foot
depth at another research project site.
Because of the extremely fine porosity of the ceramic cups soil-water
samples collected from suction lysimeters may not contain representa-
tive concentrations of participates such as bacteria and suspended
solids. Also when studying trace elements in soil water, care must
be exercised when selecting tubing, grout, plastics and the like for
these may contain impurities which might contaminate the sample.
Deep Monitoring Wells on Site. To increase the probability of obtain-
ing representative samples of groundwater leaving the irrigation
sites, nine deep wells were drilled on fracture traces'or at fracture-
trace intersections where groundwater flow is concentrated. The wells
were drilled either three inches or two and three-eights inches in
diameter to depths from 100 to 370 feet. The wells were sampled with
a mechanical hand-bailer for the first year. Six of the wells at the
Agronomy-Fores try Area were equipped with Reda electrical submergible
pumps. All but one of these became sand-locked shortly after
33
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JS
3
rt rt-
CD ?D
8 Vacuum
7, Port
«5; and
w Gauge
O
H
CO
era
^^ t
5
(W
Q
S,
00
-2-Way Pump
Plastic Tube
and Clamp
Copper
Tube
3/m" Copper-^?
•'.*.
Plastic Pipev-
24"Long
Tamped
Backfill
Super-Sil
Porous Cup
6" Hole
Bentonite
To
Vacuum
Pump
Flask
Sample
/"Bottle
Discharge
Tube
Rubber
Stopper
Plastic
Pipe
1.9"O.D.
Any Length
Porous
Ceramic
Cup
Capillary Tube
Rubber Tubing
/--Clamp
Copper Tubing
-------
installation by fine silt and sand derived from solution openings.
These pumps were replaced by Myers-type, single and double-acting
piston pumps capable of delivering 2 to 4 gpm from depths to 300 feet.
These were driven with 2-horsepower gas engines. In two wells, 2 3/8-
inch casing was set into 3-inch cased holes to screen out flowing
sand. The end of the casing was fitted with two, 2-foot lengths of
slotted Johnson well-screen capped at the bottom. A single-acting
pump barrel and copper air line were installed inside the 2 3/8-inch
casing to,a depth just above the screen.
Water levels were measured by the air-line method. Three-sixteenths-
inch copper tubing was used for the air lines in the 3-inch holes and
one-eight inch copper tubing was used in the 2 3/8-inch holes. Drop-
pipe couplings had to be grooved to make room for the air-lines
because of the small amount of clearance between the casing and drop-
pipes. In most cases copper air lines became pinched with time or
were sheared off by the vibration of pump drop pipes.
Groundwater monitoring wells also should be designed to collect rep-
resentative samples of reclaimed wastewater. This can be a problem
particularly where seasonal water table fluctuations are pronounced
(30 or more feet). Deeply cased wells, for example, may sample water
recharged in an adjacent region which underlies wastewater recharged
at the irrigation site. Such a monitoring well will not provide data
representative, of the recharged renovated wastewater (Fig 11).
Off Site Wells and Springs. An intensive program of monitoring of
private and public water supply sources was established in April of
1962 to determine the pre-test conditions and natural seasonal vari-
ations in quality of water in the area. Sampling sites included 44
private wells, five University-owned wells, six springs, and Buffalo
Run Stream, the main drainage course of Buffalo Run Valley northwest
of the project area. The identification of the wells and springs is
shown in Appendix B and their geographic location is shown in Figure 2.
The sampling program was continued at 1-month intervals for the period
April 1962 to April 1963, and at approximately 2-month intervals until
1968 and less frequently since that time. New wells have been added
to the survey from time to time and in some instances wells became dry
or sampling was discontinued. Inventory of off site water supplies
in advance of initiating irrigation projects is of value to establish
background conditions.
Soil Moisture Access Tubes. Thin-walled, steel tubes were installed
to 20-foot depths in various irrigation plots and adjacent control
plots. These were used to monitor the movement of water through the
soil mantle by the neutron scattering method. All sites were cali-
brated by determining the soil moisture content of samples collected
at 1-foot intervals during drilling. Bulk density determinations on
35
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MONITORING WELLS
MAP VIEW
(b)
Figure 11. Manitoring Wells Drilled and Cased Below Streamlines
Containing Renovated Sewage Effluent. In Mapview (b)
Wells Appear to be Properly Located.
36
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samples from the Agronomy and Forestry Areas were made by the mercury
immersion method and these were compared with field measurements
taken in place by a Nuclear-Chicago gamma radiation device.
Soil Samples. At the time of installation of the soil moisture access
tubes, soil samples were obtained at 1-foot intervals to 20 feet or
to bedrock, whichever came first. Part of the samples was used for
determining soil moisture at the time of installation and for bulk
density determinations. The remaining soil material was composited
over 5-foot intervals for chemical analysis.
Soil samples were secured at various times at 1-foot intervals to a
depth of five feet from all Agronomy and Forestry experimental plots.
These samples were air-dried, crushed to pass a sieve opening of 2 mm
for chemical analysis. Soil samples were also obtained at various
depths for special studies, both physical and chemical.
Weather Station. Two climatic stations were established specifically
for the project, one in the vicinity of each irrigation site. Instru-
ments collected data on precipitation, humidity, temperature, solar
radiation, and wind velocity.
37
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SECTION V
IRRIGATION SYSTEM OPERATION
SPRINKLER TESTING AND DEVELOPMENT
Preliminary testing of irrigation systems which could operate
throughout the winter months and yet offer reasonable distribution
patterns was done in 1963-64. Both surface and sprinkler irrigation
type distribution methods were tested and the major results discussed
in Penn State Studies No. 23 (1).
A 14-acre area in the Gamelands was first irrigated during the winter
of 1964-65 (10) using commercial and modified sprinklers. Test
results during this winter indicated that stationary deflector sprink-
lers operated exceptionally well even when temperatures dropped below
zero. The distribution pattern of this type sprinkler, however, was
not as uniform as desired. Results of that year's test work have
also been reported (1).
Two additional studies of sprinklers for distributing effluent during
freezing conditions were made. The first of these (1965-66) was on
the development of stationary-orifice, rotating-deflector sprinkler
heads (11). The sprinklers in this study used essentially the same
type of base as the stationary deflector sprinkler of 1964-65; however,
they used various types of frameworks above the base which permitted
the cone-shaped deflector to rotate hydraulically, Figures 12 and 13.
Extensive preliminary testing was conducted to establish rotor design
criteria for obtaining the optimum distribution pattern. Rotor diam-
eters of 1.5 and of 2.0 inches were chosen and each of these was test-
ed with three different slot design criteria. The purposes of the
slots were to produce proper rotation of the rotor and to aid in the
uniform distribution of the effluent. Three replicated distribution
tests using multiple sprinkler heads were conducted to determine the
uniformity coefficients of the distribution patterns produced by each
rotor configuration. These results are listed in Table 4 and show
that the best distribution was obtained with the 2-inch rotor having
3/16-inch wide slots cut into the rotor face. However, uniformity of
distribution was substantially poorer than with conventional rotating
sprinklers which have a uniformity coefficient of 75 to 80%.
The distribution pattern of the rotating-deflector sprinklers was
appreciably better than that of the stationary deflectors as long as
the rotors continued to turn. During the winter tests, however, it
was found that only 27 percent of them rotated during every run, while
8 percent never rotated and the other 65 percent varied from rotation
to non-rotation from week to week. It is believed, however, that
efficiency of turning could be greatly improved if the machined parts
were more finely finished.
39
-------
3 "RADIUS
MILLED SURFACE
t-
fOlCD
jX 2"D ROTOR
BOTTOM TURNED
TO 15° TAPER
j| SLOT, MILLED
0.070" DEEP AT
20°ANGLE
-_I
j SLOT, MILLED
0.060"DEEP AT
15° ANGLE
ALUMINUM ROTOR PIN
SUPPORT BRACKET
SECTION A-A
Figure 12. Model I - 2 Inch Rotor Sprinkler (11).
•f NFX I ± BOLT
M
g- TURNED 0.175"
TAPERED 60°
I"
y THICK ROTOR
NO. 16 OR. (0.177")
f DEEP
NO. 6 X j
MACHINE SCREW
ORIFICE CHAMFERED
«•* « ft'
BOTH ENDS
40
-------
II NPSTHRD.
2" D TAPERED BRASS CAP
•5- SLOT, MILLED 0.060
DEEP AT I5»AN6LE
3"
7g SLOT, MILLED 0.070"
DEEP AT 20°AN6LE
I" i"
|- X I y ROTOR , BOTTOM
TURNED TO 15° TAPER
I" l" i"
y NFX l-i BOLT.i TURNED
TO 0.17S "AND TAPERED 60°
NO. 6 X IA MACHINE
SCREW, 2 REO'D.
BRASS CAP
j THICK ROTOR , NO. 16 DRILL
(0.177") J"DEEP
NO. 36 DRILL , NO. 6 TAP,
2 HOLES
NOTE: ji xi"ORIFICE
CHAMFERED 45° X~"
BOTH ENDS
SECTION A-A
Figure 13. M*iel II - 1.5 Inch Rotor Sprinkler (11).
41
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Table 4. Suranary of Uniformity Coefficients from Rotor Design
Tests (11)
Sprinkler Uniformity
Model Designation Coefficient3
Rotor Diam. Slot Width
I 2.0 x 1/8 34.48
42.26
45.96
Avg. = 40.23
I 2.0 x 3/16 49.65
47.89
41.95
Avg. = 46.50
I 2.0 x 1/4 37.87
29.63
55.77
Avg. = 53.76
II 1.5 x 1/8 18.56
17.81
21.67
Avg. = 19.68
II 1.5 x 3/16 28.57
27.13
26.53
Avg. = 27.41
II 1.5 x 1/4 17.02
26.Q5
12.55
Avg. = 18.54
coefficient ^ 100(1 - 0.798 |); where S is the
standard deviation and x is the population mean. (12)
42
-------
Figure 14. Indexed Position, Part-Circle Sprinkler, Rainbird Model
35-PJ, Types E and F. (13)
43
-------
Figure 15, Random Indexing, Grooved Deflector Sprinkler, Type C.
Upper Left View Shows Deflector; Lower Left View Shows
Sprinkler Position When Not Operation; Right View Shows
Sprinkler in Operating Position. (13)
44
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The' second study (1967-68) was done on the development of sprinklers
to provide both satisfactory distribution and the penetration of exist-
ing ice or snow ground cover (13). An indexing mechanism was developed
to control the position of a part circle sprinkler during successive
runs. Figure 14. This sprinkler concentrated its discharge over a
specified sector of a circle during one run, for the next run it
advanced 120 degrees for irrigating another sector of the circle, and
so on. Even though the sprinkler base advanced 120 degrees each time
the irrigation line was turned on, the specific size of circle sector
irrigated could be established independently with a separate mech-
anism. Irrigated sectors of 120 and 240 degrees were compared.
A randomly indexed-position sprinkler using curved grooves in the
deflector to rotate the head was also developed, Figure 15. In addi-
tion to the two curved grooves, four straight grooves were machined
in the rotor to provide intermediate and long range streams of efflu-
ent. Reference marks on the sprinkler were used to determine relative
rotation between the base and the cap during each test run.
During the tests, comparisons were made of the relative penetrations
or melt-through produced by the 120-degree indexing, the randomly
indexing, and the non-indexing sprinklers. The snow pack surface
appearance with increasing degree of penetration is shown in Figure 16.
The distribution and penetration of the indexed-position part circle
sprinkler were satisfactory, however, this type sprinkler was not
acceptable because it failed to oscillate satisfactorily during freez-
ing temperatures. The randomly indexed-position sprinkler operated
and penetrated satisfactorily, but did not give as uniform a distri-
bution pattern as desired.
'Since all of the experimentally designed sprinklers were deficient in
one respect or another for winter operation and the commercially
available rotating sprinklers have peimitted reasonable operation in
the winter period, the presently operating winter system of approxi-
mately 60 acres is fitted with commercially available rotating
sprinklers.
HYDROLOGIC CONSIDERATIONS
Three intensive and detailed hydrologic investigations were made in
conjunction with this project. Two were conducted on the fine textured
soil site in the Agronomy Area (14, 16), while the other was on a
sandy soil site in the Gamelands Area (15).
The 1965-67 Runoff Investigation
Site Description and Procedures. The first study (14) was conducted
on the Reed Canarygrass Area. The soil on the area was a Hublersburg
clay loam with a slope of 3 to 8 percent. The study area was subtended
45
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a. Little Penetration (Note smooth ice layer)
b. Ifoderate Penetration (Note honeycombed effect)
c. Severe Penetration (Note complete melt-through)
Figure 16. Surface Appearance with Various Degrees of Penetration
of Snow by Effluent Applied with Different Sprinklers.
46
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by four lateral irrigation lines 800 feet long, with a staggered
spacing of sprinklers, 80 x 80, which applied two inches of wastewater
at weekly intervals. The application rate was % inch per hour. With-
in this area approximately 2.4 acres contributed surface runoff to a
90-degree V-notch weir gauging station. The permanent groundwater
table was approximately 200 feet below the soil surface in the bed
rock.
At seven sites, (S1-S7) at approximately 100-foot intervals along the
length of the slope, shallow wells (4-inch diameter perforated fiber
pipe) were installed to a depth of four feet and piezometers (3/4 inch
steel pipe) to depths of 2, 4, 6, 8 and ten feet. Piezometers are
designated by site number and depth, e.g. S1-P10 indicates Site 1 and
Piezometer at the 10-foot depth. Figures 17 and 18 show the topog-
raphy of the site and a vertical profile through the piezometer sites.
To characterize the soil properties important to its hydrologic behav-
ior infiltration rates were determined using a double ring infiltrom-
eter method as described by Slater (17). Soil cores, 3 inches in
diameter and 3 inches high were obtained at 6-inch increments to
depths up to four feet. These cores were used to determine percola-
tion rates, aeration porosity at 50 cm tension and bulk density of the
various layers, "in addition samples were collected at 6-inch inter-
vals to a depth up to ten feet using a trailer mounted hydraulic
sampler. These soil samples were used for mechanical analyses (18)
and for pore size distribution measurements using a mecury intrusion
porosimeter (19)- In conjunction with the runoff data, water samples
were taken periodically during periods of runoff at the weir to deter-
mine pH, chloride, phosphorus, nitrate and methylene blue active
substance (MBAS) content. Determination procedure? are described in
Standard Methods (20), with the exception of the chloride concentra-
tion, which was determined by using an Aminco-Cotlove Chloride
Titrator (21).
The results of the analyses of these samples were then compared with
analyses of the applied effluent as well as analyses of samples taken
at a depth of six inches, from a suction lysimeter installed at S4.
Since phosphorus is almost completely removed by six inches of soil
(8), its concentration was used in investigating the hypothesis that
surface runoff occurring after the day of irrigation was actually a
result of subsurface water flow and resulting downslope seepage.
Soil Properties. The results of infiltration determinations for S1-S7
are presented in Table 5 and represent an average of three replica-
tions. These results indicate that average infiltration rates exceed
the effluent application rate of 0.25 inches per hour.
Percolation determinations made on collected core samples indicate the
range of subsoil permeabilities at various depths and sites along the
47
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oo
Ag 10
Ag 9
Ag 7 —
v , irrigation line with sprinkler
— — — ...... location of V-Notch Weir and embankment
road culvert and ditch below Weir
._ cinder road
swampy area
•»••*••*•»••%•*•
Scale:
3/4" = 80'
Figure 17. Topographic Map of Research Area with Location of Piezometer Sites, Irrigation Lines
and V-Notch Weir.
-------
NE
80 J
£ 70
c
§ 60
•r—
40
Scale:
Horizontal 3/4" = 80'
Vertical 1" = 20'
0
80
160
240 320 400 480 560
length of slope in feet
640
720
Figure 18, Profile Diagram of Hillside with Location of Piezometer Sites.
-------
research hillside. These results are summarized in Table 6 and are
an average of three replications.
Table 5. Average Infiltration Rates at Sites 1-7.
Site
Infiltration Rate
1
2
3
4
5
6
7
Inches/hr
0.65
0.53
0.90
2.47
2.50
0.97
3.83
Table 6. Average Percolation Rates (inches per hour) at Six Inch
Intervals to Depths Listed at Sites 1-7
Depth
0-3
6-9
12-15
18-21
24-27
30-33
36-39
42-45
48-51
54-57
29.60
1.19
1.85
0.62
0.50
10.92 2.74
3.82 1.85
0.76 0.08
1.98
0.42
1.01
0.02
0.04
0.13
1.04
12.59
1.79
0.48
0.38
0.95
0.49
0.94
0.32
1.36
0.75
0.47
0.10
0.70
0.07
0.20
7.80
2.80
1.27
0.51
0.22
0.05
0.16
0.00
0.09
1.90
1.35
0.28
0.23
0.00
0.00
0.00
0.03
These results indicate soil percolation rates ranging from 29.60
inches per hour to 0.00 inches per hour. There was an inverse rela-
tionship between depth and percolation rate as given by an r value of
-0.359 which is significant at the one percent level.
Generally the percolation rates for the 0-3 inch cores exceeded the
infiltration rates except at S5 and S7, but in all cases these rates
exceeded the irrigation application rates. Only at depths greater
than 12 inches did cores show percolation rates less than irrigation
application rates (0.25 inches per hour). Percolation rates less than
0.25 inches per hour occurred at the 12-inch depth at S3, at the 18-
inch depth at S7, at the 24-inch depth at S6, at the 30-inch depth at
50
-------
S5 and at the 36-inch depth at S2. Percolation rates exceeded 0.25
inches per hour to a depth of at least 24 inches at SI and at least
30 inches at S4.
The percentages of sand, silt and clay differ considerable at different
sites and at different depths within each site. Percentages of sand
range from 8-47%, silt 12-49%, and clay 21-721. Textural class ranged
from loam to clay loam to clay. These large ranges in the three size
fractions indicate the variability present in the soil and help to
explain the differences in permeabilities at different depths.
Aeration porosity as determined at 50 cm water tension from the core
samples is summarized in Table 7. These values illustrate a range of
aeration porosity from 1.3 to 16.1 percent. These values are general-
ly quite low, especially at lower depths. Depth and aeration porosity
were negatively correlated, with an r value of -0.429 which was
highly significant.
Table 7. Average Aeration Porosity (Percent by Volume at 50 cm Water
Tension at Six Inch Intervals to Depths Listed at Sites 1-7
Depth
0-3
6-9
12-15
18-21
24-27
30-33
36-39
42-45
48-51
54-57
15.5
15.4
16.1
13.1
7.9
9.1
9.6
8.0
10.5
9.2
13.2
9.5
12.1
8.9
8.0
14.5 11.0
16.1 8.6
10.5 8.9
13.8
12.8
14.8
13.3
9.0
13.6
11.5
10.5
8.9
7.1
3.6
7.8
14.6
10.2
10.1
6.0
7.5
5.7
7.8
3.6
5.2
7.3
11.0
8.4
5.7
1.3
1.5
3.7
6.3
A correlation analysis indicated a positive significant correlation
of aeration porosity and percolation rates. However, the rz value of
0.05 indicates a considerable residual variation in percolation rate
which may not be associated with aeration porosity.
Bulk densities were also determined for the soil cores and are present-
ed in Table 8. These values ranged from 1.17 grams per cc to 1.70
grams per cc and showed highly significant correlations as follows: a
positive r value for depth of 0.492, a negative r value for aeration
porosity of -0.337, and a negative r value for percolation rates of
-0.301.
51
-------
Table 8. Bulk Density (grams per cc) at Six Inch Intervals To
Depths Listed at Sites 1-7
Depth
0-3
6-9
12-15
18-21
24-27
30-33
36-39
42-45
48-51
54-57
1.37
1.38
1.30
1.17
1.36
1.47
1.53
1.56
1.54
1.50
1.54
1.52
1.58
1.54
1.54
1.36
1.43
1.57
1.26
1.41
1.53
1.62
1.64
1.70
1.30
1.31
1.40
1.52
1.56
1.62
1.66
1.66
1.66
1.45
1.66
1.60
1.68
1.65
1.58
1.43
1.50
1.50
1.32
1.32
1.37
1.49
1.61
1.53
1.52
1.58
Pore size distribution was determined in fragments from soil samples
obtained by the hydraulic sampler and are expressed in Table 9 as the
percentage of total porosity; porosity between 175 and 10 microns in
diameter and; porosity between 10 and 0.10 microns. The larger pores
best characterize the water relationship in terms of water movement
and temporary storage within the soil. The smaller pores characterize
the more permanent storage capacity.
The much smaller intra-fragment porosity in the size range 175 to 10
microns determined by the mercury intrusion procedure, when compared
with the aeration porosity as determined in the cores, indicates that
many of the larger pores (>60 microns) characterized by the 50 centi-
meter tension value are inter-fragment or inter-ped in character.
The percentages of total porosity in Table 9 were calculated from bulk
density values determined for soil clods or peds used in the mercury
intrusion porosimeter study. Since the inter-fragmental pore space
was not measured and the fragments were oven dried, the porosimeter
bulk densities are considerably higher than the core bulk densities
and consequently result in lower total porosity values.
Hydrologic Measurements.
Shallow Wells. Measurements from the shallow wells definitely indi-
cated the presence of perched water table conditions over the entire
research area. Throughout the entire period, August 1965 - July 1967,
the wells at SI, S3, S4 and S7 continuously showed free water levels
within four feet of the soil surface. The well at S5 became dry only
if irrigation was delayed for one or more weeks. The wells at S2 and
52
-------
Table 9. Percentages of Total Porosity, Porosity from 175 to 10 Microns and from 10 to 0.10
Microns-in Diameter for Sites 1-7 at the Given Depth Intervals
Ul
Depth
Intervals (inches)
Site 1
Porosity Fraction
Total
175-10
10-. 10
0
40.5
4.3
29.5
6
41.2
5.4
30.5
12
51.4
9.1
27.4
18
36.7
4.4
20.1
24
34.4
1,2
.20.5
30 36
29.9 32.1
1.8 0.9
17.2 19.0
42
34.4
1.9
19.9
48
37.0
0.7
22.6
54
31.0
1.0
4.6
60
32.5
1.5
17.4
66
30.6
1.5
7.2
Site 2
Porosity Fraction
Total
175-10
10-. 10
Porosity Fraction
Total
175-10
10-. 10
Porosity Fraction
Total
175-10
10-. 10
Porosity Fraction
Total
175-10
10-. 10
0
35.9
5.2
20.0
66
31.0
1.8
14.9
0
43.8
4.4
32.5
48
31.4
2.3
10.1
6
28.0
3.1
16.6
72
34.0
3.3
13.9
6
40.8
3.2
27.2
54
30.2
1.9
9.4
12
32.1
3.4
11.5
78
35.5
2.9
13.9
12
38.5
4.6
16.5
60
29.5
1.6
12.1
18
26.1
1.9
12.7
84
32.5
2.5
14.4
18
28.7
3.3
17.0
66
30.2
3.0
10.6
24
31.0
1.8
6.8
90
33.2
1.2
12.2
Site
24
30.6
4.3
12.9
72
29.9
2.9
13.2
30 36
29.0 36.9
3.2 0.8
9.3 6.0
96 102
30.2 31.0
1.5 0.9
10.0 11.9
3
30 36
29.5 28.7
3.4 2.6
9.8 11.3
78 84
30.2 30.2
2.9 0.7
11.2 11.1
42
37.8
0.7
5.3
108
31.7
0.9
10.2
42
29.1
2.4
9.8
48
37.8
1.0
5.3
114
32.1
1.2
7.5
54
39.3
0.7
4.7
120
32.1
0.8
7.0
60
31.0
1.3
9.0
126
32'. 1
0.9
10.1
-------
Table 9. (continued)
tn
Porosity Fraction
Total
175-10
10-. 10
Porosity Fraction
Total
175-10
10-. 10
Porosity Fraction
Total
175-10
10-. 10
Porosity Fraction
Total
175-10
10-. 10
Porosity Fraction
Total
175-10
10-. 10
43
2
34
31
1
16
43
3
31
29
2
14
29
0
6
0
.1
.6
.1
48
.0
.5
.4
0
.4
.8
.7
0
.9
.5
.6
54
.9
.9
.8
43
2
32
24
1
17
38
1
27
34
2
7
35
0
6
6
.4
.7
.8
54
.6
.4
.6
6
.5
.9
.7
6
.8
.0
.9
60
.5
.4
.0
12
32.5
1.6
11.5
60
28.7
0.9
13. 2
12
35.5
2.2
18.2
12
32.1
1.4
7.5
66
33.6
0.8
6.6
18
32.3
2.3
6.0
66
31.0
0.9
7.7
18
32.5
2.9
14.4
18
31.0
2.2
14.1
72
38.5
0.4
5.0
Depth
Site
24
28.7
2.7
5.2
72
30.6
1.3
4.2
Site
24
32.9
2.5
16.9
Site
24
31.0
0.9
5.4
78
37.0
0.5
6.8
Intervals -(inches)
4
30
29.9
1.1
3.9
78
36.9
1.1
3.6
5
30
26.1
0.9
4.9
6
30
34.0
1.4
5.8
84
37.0
0.5
2.8
36
28.7
1.0
12.7
84
35.1
1.4
6.0
36
26.1
1.0
5.5
36
34.8
0.9
4.7
90
34.8
0.5
3.6
42
26.8
1.2
8.8
90
35.9
1.3
9.0
42
32.9
3.0
8.7
42
33.6
1.1
4.3
96
32.9
0.4
6.4
48
31.0
1.9
5.4
48
35.1
2.5
8.9
102
35.1
1.1
5.6
-------
Table 9. (continued)
•" • • .^^^^^^^^^^ mmmmimmmm ••...^•.^••••^^•••^•M
MBVOPW^W^^^H
^^•^^•MM
to^^^^^^
^iiVMM^^B^HHHW^^H
^^•^^•.^H^A^^VhH*
^^M^^^^VM^VM
Depth
- _ _ ..." -T •_ 1 •• " " ' ' ' " ™
Intervals (inches)
Site 7
Porosity Fraction
Total
175-10
10-. 10
Porosity Fraction
Total
175-10
10-. 10
40
3
29
29
0
6
0
.0
.1
.9
48
.5
.6
.2
37
4
27
30
0
5
6
.8
.3
.5
54
.2
.8
.8
12
41.2
2.2
33.0
60
28.7
0.8
15.6
18
29.5
0.7
17.9
66
30.2
0.8
7.4
24
29.5
3.8
10.7
72
29.2
0.8
15.1
28
0
17
31
1
17
30
.4
.7
.2
78
.7
.4
.1
36
27.2
1.3
16.5
84
34.0
0.5
3.7
42
30.6
0.7
6.7
en
tn
-------
S6 were the only ones which became dry within weekly irrigation inter-
vals, and this occurred only during the summer and early fall.
Due to higher rates of evaporation and transpiration during the
growing season, water levels in the wells were much lower than during
the fall and winter. The typical responses of the shallow wells to
irrigation are presented in Table 10. The 4/17 readings were taken
immediately proceeding irrigation. The times of measurement of the
values shown in Table 10, expressed as time in hours after termination
of irrigation, are given in Table 11. As indicated, water levels
approach the soil surface during and immediately after irrigation and
then decline until rainfall or irrigation occurs again. These changes
in water levels are illustrated in Figures 19 and 20.
Table 10. Shallow Well Elevations for Sites 1-7 on April 17-21, 1967
Date 1234
4/17
4/18
4/19
4/20
4/21
48.14
50.80
50.53
50.05
47.79
52.62
56.15
55.46
54.27
53.57
57.68
59.18
58.87
58.18
58.01
58.39
60.35
60.15
59.79
59.55
61.48
63.95
64.54
63.78
63.28
DRY
66.73
66.00
65.84
DRY
62.07
64.49
63.73
62.91
62.53
Table 11. Time in Hours After Termination of Irrigation for Shallow
Well Readings Presented in Table 10
Sites 4/18 4/19 4/20 4/21
1, 2
3, 4, 5,
6, 7
3
11
27"
35
55
63
79
87
Field observations early in the summer of 1967 indicated that perched
water table conditions may exist continuously at depths below the
shallow wells. The conditions which lead to this conclusion were as
follows. As a result of no effluent applications from June 5 to
July 6, 1967 and a low rainfall total of 2 3/4 inches, all shallow
wells became dry. This indicated that no perched water table existed
at a depth of four feet below the soil surface. However after a two
inch application on July 7, water levels were observed in all wells.
Then after an additional application on July 10, surface runoff was
56
-------
51.0
50.0
49.0
48.0
c 61.0
g 60.0
I 59.0
5 58.0
65.0
64.0
63.0
62.0
4/17
Site 1
Site 4
Site 7
4/18
4/19
4/20
4/21
Dates
(Plotted to Scale)
Figure 19. Shallow Well Water Level Elevations at Three Sites
Showing Typical Responses to Irrigation on 4/17/67
with Two Inches of Sewage Effluent.
57
-------
tn
OO
cu
80
70
60
50
40
Scale:
Horizontal
Vertical
3/4"
1"
80'
20'
0
80
160 240 320 400 480
length of slope in feet
560
640
720
Figure 20. Cross Section of Hillside Showing Increase in Elevation of Perched Water Table
(cross hatched area) 12 Hours After 2" Irrigation.
-------
observed and all wells, with the exception of the well at S6, showed
water levels at a height approximately equal to the ground surface.
Only two possibilities exist to explain this situation. Either the
perched water table persisted immediately below the depth of the
shallow wells; or, the material slightly below the bottom of the
wells is so impermeable that the perched water table is formed at
this level.
A specific study of the actual change in water levels due to irriga-
tion and rainfall was made to relate the well data to the nature of
water movement on the hillside slope. The water level elevations
for this study are presented in Table 12. The decline in the wells
at the various sites was calculated as the difference between the
elevations taken on July 18 at 8:00 a.m. (peak value) and on July 21
at 12:00 noon (final elevation).
Table 12. Water Level Elevations (feet) with Respect to Irrigation
and Rainfall at Sites 1-7
Date and Time
Site
1
2
3
4
5
6
7
7/17
4 p.m.
47.93
<52.65
57.90
59.36
61.87
<65.82
61.87
7/18
8 a.m.
50.78
56.37
59.14
60.34
65.11
66.85
64.44
7/18
4 p.m.
50.73
56.14
59.12
60.29
65.03
66.24
64.25
7/19
4 p.m.
50.53
55.57
59.01
60.22
64.66
<65.82
63.60
7/20
12 noon
50.68
55.54
59.13
60.38
64.73
65.83
63.63
7/21
12 noon
50.55
54.81
58.99
60.32
64.26
<65.82
63.11
REMARKS: 1. Irrigation 7/17, 4 p.m. to 12 midnite for lines Ag 8 and 9;
irrigation 7/18, 12 midnite to 8 a.m. for lines Ag 7 and 10,
2. .35 and .12 inches rainfall in a 24-hour interval
before readings taken on 7/20 and 7/21, respectively.
Table 12 is summarized in Table 13 which lists the total decline for
each well along with the order of magnitude of decline with one indi-
cating the highest and seven the lowest. It was noted that the rates
of decline are lowest in the areas of SI, S3, and S4 which indicates
low permeabilities and/or seepage into these areas. Seepage into SI
probably originates from the area near S2. Seepage into S3 and S4
probably originates from the upslope area near S5 and S6. Calcula-
tions involving limiting peimeability and capacity of the soil to
store and transmit water were made for various sites using infiltra-
tion rates, percolation rates, and aeration porosity. As previously
59
-------
Table 13. Total Declines in Water Levels of Shallow Wells in Feet
and Order of Rapidity of Decline in Water Levels by
Sites 1-7
Total Decline 0.23 1.56 0.15 0.02 0.08 >1.03 1.33
Order of „
Decline 5 2 6 7 4 ld 3
data were used which indicated that S6 showed the most rapid
decline.
discussed, only at S3 is the soil percolation limiting; and, at no
site is infiltration limiting the capacity, of the soil to store and
transmit the two inches of effluent irrigation.
The 50 centimeter aeration porosity value was used in determining the
capacity of the soil to store water. Calculations indicated that if
the water was drained from the soil pores at a tension of 50 centi-
meters (i.e., pores at least 50 cm above the perched or groundwater
table) to a depth of two feet prior to irrigation that the capacity of
this two-foot soil layer would be more than adequate to temporarily
store the two-inch application of effluent.
Values for aeration porosity were available for six- inch increments
to a depth of 54 inches at S2 and at the same increments to a depth
of 30 inches at S4. These were used to calculate the actual devia-
tions from the above situation in the field and are presented as
examples in Table 14.
The water storage capacity of the soil, for specific perched water
table conditions, was determined by measuring the distance from the
soil surface to the surface of the perched water table before irriga-
tion as illustrated in Figure 21. Assuming no water storing capacity
in the soil at a distance less than 20 inches (50 on) from the
perched water table and storage capacity equal to the 50 centimeter
tension aeration porosity at a distance greater than 20 inches above
the perched water table, one can then compute the potential storage
capacity. This can be related to the actual storage capacity as
represented by the change in elevation of the perched water table
induced by the two inch application of effluent.
The following examples of the above procedure were calculated for S2
and S4 using data presented in Table 14 and Figure 21. Since only
60
-------
Soil Surface
Perched Water Table
Where:
X
Y
Z
Distance from Perched water table to soil surface
Cm tension for aeration porosity values (50 cm = 20")
Thickness of soil under y cm tension (x - y)
Calculation:
X
Y
Z
Site 2
44"
20"
24"
Site 4
24"
20"
4"
Storage capacity calculated for Z thickness from Table X
Site 2 = 2.24"
Site 4 = 0.44"
Figure 21. Calculation of Water Storing Capacity of the Soil Above the Perched Water Table
for Sites 2 and 4.
-------
Table 14. Aeration Porosity and Water Storage Values for Six-Inch
Depth Increments in the Soils at Sites 2 and 4
Inches
50 cm Tension
Aeration Porosity
Site 2 Site 4
Water Storage
Site 2 Site 4
Cumulative
Water Storage
Site 2 Site 4
in.
in.
in.
in.
0-6
6-12
12-18
18-24
24-30
30-36
36-42
42-48
48-54
9.1
9.6
8.0
10.5
9.2
13.2
9.5
12.1
8.9
11.0
8.6
8.9
13.8
12.8
0.55
0.58
0.48
0.63
0.55
0.79
0.57
0.73
0.53
0.66
0.52
0.53
0.83
0.77
0.55
1.13
1.61
2.24
2.79
3.58
4.15
4.88
5.41
0.66
1.18
1.71
2.54
two inches of effluent were applied either the aeration porosity over-
estimated the storage capacity or additional water was entering the
site by runoff or seepage. At S4 a total of only 0.44 inches was
needed to increase the elevation of the perched, water table from a
depth of 24 inches to the soil surface. As a result of this situa-
tion, where the water applied exceeded the water storage by
approximately 1.5 inches, water is forced to flow downslope as surface
runoff or as subsurface flow and resulting seepage or both. There-
fore, it is obvious that S4 and the surrounding area, under these
particular conditions, serves as a source of additional water to the
lower portion of the hillside.
Piezometers. Piezometers were installed at two, four, six, eight,
and ten foot depths at each of the seven sites. These installations
measured hydraulic heads at various positions along the hillside.
They were used in determining the direction of water movement at the
sites and were also used in measuring permeability by the falling head
method (22, 23). The permeabilities were measured on July 11, 1967,
using the falling head method described by Kirkham (23). It should
be noted that the procedures used are commonly based on the rate of
seepage into the piezometer, but according to Kirkham, the same pro-
cedure is applicable to the falling head method, where a head is
established within the pipe and recedes as water flows from the pipe.
The following conditions must be fulfilled in order to use this
method. The base of the piezometer must be below the water table and
the water level in the piezometer must be at least 20 centimeters
(8 inches) above the water table. These conditions were fulfilled
at the time of measurement. After calculating the time (t£ - t]_) and
the ratio of the effective heads (h^ / b.2), as given in the perme-
ability equation (6) the permeabilities were read directly from a
62
-------
nomograph (6). These results are presented in Table 15.
These data indicate that 25 piezometers had permeabilities of less
than 0.014 in. per hour. A comparison of these permeability values
with the time of peak piezometer response to irrigation, shown in
Figures 22-28 indicates that in all examples where the peak response
was only 1 or 2 days after irrigation, the permeabilities were 0.70
inches per hour or greater. However, S7 - P? exhibited a perme-
ability value of 1.13 inches per hour but did not reach a peak
until the fourth day. This delay may be due to a delay in input of
water from adjacent higher elevations.
A correlation was made between the permeability values in Table 15
and the various soil properties, as determined from the samples col-
lected by the hydraulic soil sampler. The correlation coefficients
are presented in Table 16.
Table 15. Soil Permeabilities Determined on July 11, 1967 by the
Piezometric Method for All Piezometers at Sites 1-7
Piezometer
Inches Per Hour
p
P8
P6
P4
P2
a
a
a
4.25
2.83
1.42
a
2.83
0.01
a
a
a
a
a
0.04
0.07
a
a
a
0.71
a
a
a
a
a
a
a
a
0.70
a
a
a
a
a
1.13
Values less than the lowest values on the nomograph CO.014 in./hour)
Table 16. Correlation Coefficients Relating Soil Permeability and
Various Soil Properties
Bulk Large I %
Density Pores Silt Clay
Permeability -0.380 0.223 0.441* -0.328
The correlation of percent silt with permeability was significant at
the five percent level. Other correlation coefficients were non-
significant. A negative correlation coefficient (-0.579) showing
significance at the one percent level was found between the percentage
63
-------
51
50
49
48.
47-
46
45
44
Soil Surface
10
8
26 27 28 29 30
December
23 45
January
Figure 22. Water Level Elevations in Piezometers at Site 1 for Two Observation Intervals, 1966-67.
-------
t/i
Soil Surface
51
27 28 29
December
30
23456
January
Figure 23. Water Level Elevations in Piezometers at Site 2 for Two Observation Intervals, 1966-67.
-------
59
58
57
c
o
I 55
-------
611
••^-••A _Soi1 Surface £
eak J """""*"
59'
58
O)
•r—
-M
fO
I 56
55
. A
26 27 28 29
December
30
23456
January
Figure 25, .Water Level Elevations in Piezometers at Site 4 for Two Observation Intervals, 1966-67.
-------
00
65
64
63
62
61
O)
-------
70-t Soil Surface
vo
69
68'
67
66
I 65
n 64
63
62
61
60
10
26 27 28 29 30
December
23456
January
Figure 27, Water Level Elevations in Piezometers at Site 6 for Two Observation Intervals, 1966-67.
-------
65
64
63
Soil Surface
OJ
O!
c
o
62
-------
of clay and large pores. Correlation coefficients significant at the
five percent level were found between percent sand and large pores
(0.494), between clay and bulk density (-0.465), and between large
pores and depth (-0.506). The nature and direction of subsurface
water movement with respect to the soil surface and the perched water
table will be interpreted from the water level elevations for January
1-6, 1967 (see Table 17). These data represent the study area during
a period of high moisture content. The direction of water movement
at the base of each piezometer was determined from the head differ-
ence in adjacent piezometers and is represented by arrows at each
site in Figures 29-32. The permeabilities indicated in these figures
were classified according to the following criteria:
i
1, Any zone with a piezometer permeability value greater than
0.014 inches per hour, was considered permeable and Was
indicated by the respective piezometer permeability value.
2. Zones with piezometer permeability values less than 0.014
inches per hour were subdivided as follows:
a. Impermeable - zones with piezometer water level changes
of less than 0.05 foot per 100 hours.
b. Low permeability - zones with piezometer water level
changes greater than 0.05 but less than 1.00 foot per
100 hours.
c. Permeable - zones with piezometer water level changes
greater than 1.00 foot per 100 hours.
• The category 2c designates some of the piezometers with permeabilities
less than 0.014 inches per hour by the Kirkham falling head method as
being permeable due to large changes in hydraulic head during the 100
hour period.
->
Table 17. Peak Water Level Elevations for Shallow Wells and Piezom-
eters fdr the Interval 1/2 - 1/6/67 at Sites 1-7
Measuring
Device
PIO
P8
P*
P4
Well
1
50.00
44.37
47.82
51.74
51.56
51.42
2
53.36
53.26
54.99
52.52
54.12
56.03
3
51.74
55.54
54.18
56.58
59.19
59.24
4
54.77
54.19
57.00
60.28
60.86
60.77
5
56.67
60.67
a
64.18
64.01
65.20
6
60.30
63.99
65.81
66.81
67.72
67.42
7
a
60.33
63.40
64.23
63.87
65.06
NO data available.
71
-------
0)
2.83
4.25
<0.01
<0.01
<0.01
Water level
in piezometer
Impermeable
layer
Low permeable
layer
Soil surface
Perched water
table
Figure 29. Set of Piezometers at Site 1 Showing Limitijig
Permeability, Perched Water Table, Water Levels in
Piezometers and Predicted Directions of Movement.
72
-------
CM
O)
4J
•p—
CO
0.01
2.83
1.42
CO
Ol
4->
•r—
CO
0.01
<0.01
<0.01
<0.01
<0.01
Figure 30, Same as Figure 29 but at Sites 2 and 3.
73
-------
0.71
<0.01
<0.01
<0.01
0.07
LO
I/O
-------
ft.
-------
On the basis of the head difference in adjacent piezometers it was
found that artesian pressures were present in one or more zones at
each site except S6 which topographically represented the highest
elevation on the slope. Depths where these artesian pressures were
indicated are as follows: SI - two and ten feet, S2 - six and ten
feet, S3 - eight feet, S4 - ten feet, S5 - four feet, S7 - four feet.
All other directions of water movement were downward with the excep-
tion of SI and S4 at the upper two feet where movement was horizontal.
In evaluating these directions of water movement, at several sites
where strong trends were not indicated, additional data were used to
more fully characterize the situation. These data are presented as
graphs in Figure 33 and represent the two and four foot piezometers
at sites 1, 5, and 7. At SI in Figure 33, water levels in ?4 are
slightly higher than, are equal to, or are less than levels in ?2.
These levels, taken from data for August 15 to September 9, 1966,
indicate that at various times water was moving horizontally, down-
ward, or upward. For S5 in Figure 33, data show that water levels in
?2 are always higher than levels in ?4. This indicates that water
movement is downward. For S7, data indicate an upward movement of
water for the period December 5 to December 23, 1966. This is indi-
cated by water levels in ?4 which are higher than those in ?2.
These changes in direction of water movement in the upper four feet of
the soil are a result of changes in head at these levels. Since these
heads can change more readily in this upper zone, as a result of rain-
fall or irrigation, the direction of water movement can also be
altered.
Surface Runoff and Related Measurements. A final phase of the hydro-
logic measurements included the determination of rates and magnitude
of surface runoff, factors affecting these measurements, and the
analysis of runoff samples. Surface.runoff was measured by a 90°
V-notch weir previously described. Data were difficult to obtain
during the winter, due to freezing conditions at the weir and in the
stilling basin at the water level recorder. Peak discharge rates
were determined during the operation of irrigation lines Ag 8 and 9
using a value of 1.8 acres as the area contributing to this runoff
rate. The value for total runoff and the percentage of the total
applied is calculated for the area of 2.4 acres. This area contrib-
uted water to the measuring station and was irrigated by irrigation
lines Ag 7, 8, 9 and 10. Table 18 summarizes the runoff data secured
from December 12, 1966 to July 11, 1967. The missing weekly intervals
were due to freezing conditions, equipment failure, and intervals when
irrigation was not carried on prior to and during a harvest period.
The above runoff data indicated a wide range in the amounts of total
runoff. The range in this table is from 100 percent (54,230 gallons
per acre) to 11 percent (6,168 gallons per acre). Also, irrigation
76
-------
SI
51,
50,
49,
48
64.
63.
55
62
15 16 17 18 19
22 23 24 25 26
August
29 30 31
65.
S7 64.
63
56789
12 13 14 16
December
19 20 21 22 23
Figure 33. Piezometer Water Level Elevations (feet) at Several
Sites in 1966.
77
-------
Table 18. Surface Runoff Expressed as Peak Discharge (gpm per acre),
Total Discharge (gal./acre), and Percent of the Total
Application for the Indicated Dates.
Date
12/12/66
1/3/67
1/10/67
1/24/67
3/24/67
3/28/67
5/15/67
5/22/67
5/29/67
7/11/67
Peak Discharge
(gpm/acre)
76
100
111
111
111
81
72
39
56
31
Total Discharge
(gal . /acre)
24,120
28,425
33,720
27,832
54,230
42,202
28,506
6,168
16,678
14,031
Percent
of Total
Applied
44
52
62
51
100
78
52
11
31
26
periods free from runoff have been observed during most of the growing
season when much water was being lost from the soil by evapotranspir-
ation. The highest values for runoff occurred when the soil was
frozen and air temperatures were above freezing. When air temperatures
were below freezing, the effluent could freeze on the soil surface in
amounts which could considerably reduce the amount of total runoff.
When air temperatures were higher than approximately 35°F, the efflu-
ent could not freeze but also could not infiltrate into the frozen
soil. Therefore, under these conditions amounts of total runoff were
high. Also, if air temperatures were quite warm, existing snow and
ice on the soil melted and contributed additional water to the total
runoff. Generally throughout the months when no frost or freezing was
observed, the quantity of runoff was primarily influenced by the amount
of rainfall and the water utilized by the reed canarygrass, as well as
that lost by evaporation directly by the soil.
In conjunction with surf ace' runoff measurements, soil temperature
readings were taken during the fall and winter of 1966-67. This was
done in part to determine: time and extent of frost and its effect
on infiltration and surface runoff; and also to determine the effects
of effluent applications on soil temperatures. These effects are
exemplified by three specific examples which compare air temperature,
soil temperature and soil frost conditions prior to and after irriga-
tion. The resulting soil temperature and soil frost condition were
related to the total runoff. In all examples, the temperature of
the effluent as it left the sprinkler was 40-45°F. On December 12,
1966 (A) the weather had been warm prior to irrigation. No frost
78
-------
layers were present in the soil. On December 5, 1966 (B) the weather
had been cold prior to irrigation and a frost layer was present at
all sites before irrigation. After irrigation the frost layer had
melted at S5 - S7, but was still present at sites 1-4. The tempera-
ture on the day of irrigation ranged from 26-33°. On December 26,
1966 (C) the weather had been and was below freezing before, during,
and after irrigation. Soil frost and surface ice and snow were
present before and after irrigation. Table 19 summarizes the effects
of irrigation on soil temperatures in these examples. It is indicated
from these examples that various situations with respect to these
involved factors can occur, and no one broad generalization can be
made. These results show that in A with warm soil conditions and
freezing temperatures the day of irrigation, the soil temperatures
decrease considerably. In B with a frost layer present and tempera-
tures near 32°F, soil temperatures increased near the surface (within
the first eight inches) but decreased below this level. In C with
below freezing temperatures before, during, and after irrigation
little infiltration occurred and as a result soil temperatures remained
nearly constant.
Table 19. Soil Temperatures Averaged for 7 Sites at Various Depths
Before and After Irrigation for Examples A, B, and C
A
Depth
(inches)
2
4
8
12
18
Before
S1-S7
39.9
39.2
39.9
41.1
42.6
After
S1-S7
36.0
36.4
37.3
38.5
40.1
B
Before
S1-S4 S5-S7
32.9
33.9
35.2
37.2
39.1
32.7
35.2
35.8
37.8
40.0
C
After
S1-S4 S5-S7
34.0
34.2
35.4
36.5
38.0
36.2
35.0
36.3
37.3
38.0
Before
S1-S7
32.9
33.9
34.8
35.9
37.4
After
S1-S7
32.8
33.6
34.8
35.7
37.1
Data relating runoff, air temperature, and frost conditions for
12/12/66, 1/3/67 and 1/24/67 are summarized in Table 20. The air
temperature represents the maximum and minimum on the day of irriga-
tion. The runoff is expressed as a percentage of the total applied.
The temperature range and field conditions for December 12 and January
3 indicate that a fairly high percentage of the effluent must have
frozen during and shortly after application. Since a frost layer
existed before and after irrigation on January 3, infiltration would
have been very low but the runoff percentage was only 521. Therefore
under conditions favorable for freezing of the applied effluent, the
magnitude of runoff was considerably reduced or at least delayed until
79
-------
Table 20. Effects of Air Temperature and 89il Frost Conditions on
Surface Runoff for Three Irrigation Applications
Date
12/12
1/3
1/24
% Runoff
44
52
51
Frost
Before
Irrigation
Absent
Present
Present
Layer
After
Irrigation
Absent
Present
Absent
Air Temp
mm
16
25
48
C°F.)
max
27
40
64
melting occurred. Also the melting of previously frozen applications
of effluent may result in an apparent total runoff percentage of
greater than 100. This situation must be considered, if capacities
of structures designed to handle runoff are being considered in a
winter irrigation system.
The duration of apparent surface runoff is extremely interesting in
this investigation. Runoff has been recorded as long as 3 days after
irrigation ceased in many instances, with no intervention of rainfall.
Table 21 lists several examples of this prolonged runoff during which
a measurable height of water was flowing over the V-notch weir.
Table 21. Total Duration of Runoff from 2-Inch Irrigation and
Duration After Termination of Irrigation
Duration of Runoff
Hours After Termination
Irrigation Dates Total of Irrigation
5/15
5/22
5/27
51
33
36
35
22
23
This long duration of runoff indicates that subsurface flow is a part
of the total runoff. This idea was substantiated by studying two of
the composite hydrographs presented in Figures 34 and 35. This was
accomplished by estimating the surface runoff component from character-
istics of the composite curve, and by extrapolating the declining limb.
Next, by subtraction, the subsurface component was defined. Calcula-
tions for these two examples on May 22, and May 29, show that 75 and
63 percent respectively, of the total measured runoff consisted of
80
-------
oo
0.00
4 pm 1
5/15
8 pm
5/17
1 - 8 hour irrigation by Ag 8 and 9 with peak A
2-8 hour irrigation by Ag 7 and 10 with peak B
3, 4, 5 - successive 12 hour periods after irrigation
Shaded area represents extrapolated surface runoff curve
Area under dashed line represents subsurface flow
Figure 34. Runoff Hydrograph for Interval Beginning on May 15, 1967.
-------
<*-•
00
1 - 8 hour irrigation by Ag 8 and 9 with peak A
2-8 hour irrigation by Ag 7 and 10 with peak B
3, 4 - successive 12 hour periods after irrigation
Shaded area represents extrapolated surface runoff curve
Area under dashed line represents subsurface flow
Figure 35. Runoff Hyxlrograph for Interval Beginning on May 23, 1967.
-------
subsurface water flow. These values indicate that a large portion of
the total runoff can be attributed to subsurface water movement and
seepage.
If the contribution of- subsurface flow is. large, the phosphorus con-
tent should decrease, as the percentage of surface runoff decreases
and the percentage of subsurface flow increases, until all the runoff
is subsurface in origin. Data obtained during the period January 31
to February 2, 1967 were used in determining the phosphorus concentra-
tions of samples taken at various time intervals during the period of
runoff. The concentrations of phosphorus in the effluent and the 6
inch suction lysimeter, at site 4, were taken from data of January 26.
These results are summarized in Table 22 and support the theory that
runoff consists of large amounts of subsurface seepage and lateral
water movement.
The hydrologic conditions of the research area are summarized in
Figure 36. This figure indicates the areas where apparent seepage
has caused wet surface conditions on the second day after irrigation*
These wet conditions relate the effects of perched water conditions
and subsurface water movement to the observed surface wetness.
Table 22. Phosphorus Content in Applied Effluent, in a 6 In. Suction
Lysimeter, and in Total Runoff at Different Times
Expressed as Hours After Irrigation Had Terminated
Description of Sample P Content (Mg/liter)
Pure Effluent 11.425
Suction Lysimeter 0.094
6 hours (runoff) 8.750
9 hours (runoff) 6.525
24 hours (runoff) 3.925
33 hours (runoff) 2.275
48 hours (runoff) 1.275
57 hours (runoff) 1.275
-~ -*
•i
As a result of the application of two inches of sewage effluent per
week, the previously existing drainage pattern was altered. Because
of heterogeneous soil conditions consisting of irregular clay layers
of low permeability, perched water conditions resulted.
The presence of these perched water conditions near the surface was
responsible for a reduction in the ability of the soil to temporarily
store or transmit water. This capacity for water storage and trans-
mission had been so greatly reduced, especially during wet seasons,
83
-------
00
irrigation line with sprinklers
location of V-Notch Weir and embankment
road culvert and ditch below Weir
cinder road
area of surface wetness
Figure 36. Topographic Map with Seepage Areas Delineated by Shading Iwo Days After Irrigation.
-------
that applications of two inches of sewage effluent, at rates of 0.25
inches per hour, caused considerable quantities of total runoff. This
runoff consisted of surface runoff and subsurface flow which reappeared
down slope as seepage, and consequently contributed to the total run-
off. This runoff as subsurface flow persisted for several days after
irrigation under wet conditions. The perched water table, which is
usually at the ground surface, if runoff does occur, slowly declined
until the soil water conditions were such that hydraulic gradients no
longer were strong enough to cause this lateral subsurface flow and
resulting seepage. The above description of the drainage conditions,
as well as the underlying causes and conditions discussed, represent
the results of this hydrologic investigation.
The 1966-1967 Runoff Investigation
Site Description and Procedures. This study in the Gamelands Area
included approximately 2.5 acres of a Morrison sandy loam soil with
a vegetative covering of red clover. Piezometers were installed on
2-foot centers at depths of 2, 4, 6, 8, and 10 feet at each of five
stations on approximately 40-foot intervals from top to bottom of the
watershed. Diversions about 8 inches deep were installed at the base
of the slope to intercept both surface and shallow subsurface flow
and conduct it to a V-notch weir equipped with a stilling well and
liquid level recorder. Rainfall records were obtained from a nearby
U.S. Weather Bureau type, 8-inch rain gage. Three test cycles were
included in this study and occurred respectively in October-November,
1966 (Cycle I); March-April, 1967 (Cycle II), and June-July, 1967
(Cycle III). Each cycle was composed of six runs occurring at weekly
intervals. The amount applied per run was increased by 1 inch each
week from 1" the first week to 6" the last week, however, the appli-
cation rate always was kept at 0.25 inches per hour. The run number
corresponds to the depth of irrigation water applied that week.
Runoff from the watershed consisted of surface flow, subsurface flow
within the 8-inch surface layer and interflow. Interflow is defined
as water which first infiltrated and then, after moving laterally,
reappeared on the surface.
Hydrologic Measurements. The amount of precipitation that occurred
during the week prior to irrigation for each of the runs and the run-
off for all cycles, presented as percentage of irrigation amount
appearing as runoff (R/I), are shown in Table 23.
The largest average percentage of irrigation appearing as runoff
occurred in Cycle II; the smallest occurred in Cycle III. This
occurred even though more total precipitation fell in the weeks prior
to each run in Cycle III (7.71 inches) than in Cycle II (5.77 inches).
The probable reason for the lower percentage of runoff during Cycle
III was that this cycle occurred in June and July during which time
85
-------
the crop and climatic conditions caused a much greater evapotranspir-
ation loss than in March and April of Cycle II. The maximum percent
runoff (26.21) occurred in Run 2 of Cycle II, and was associated with
a seven-day antecedent precipitation of 3.44 inches.
Table 23. Percentage of Irrigation Amount Appearing as Runoff (R/I)
and Inches of Total Precipitation which Occurred During
the Week Prior to Irrigation for all Cycles
Cycle I
(Oct-Nov)
Runs Antecedent
Runoff Precip
Cycle II
(Mar-Apr)
Antecedent
Runoff Precip
Cycle III
(June-July)
Antecedent
Runoff Precip
1
2
3
4
5
6
percent
0.0
4.1
11.7
20.4
25.0
19.0
inches
0.16
0.40
0.00
0.38
1.27
0.00
percent
9.0
26.2
18.0
13.4
14.0
16.4
inches
0.23
3.44
0.91
0.51
0.35
0.27
percent
0.0
0.0
3.5
8.9
17.4
21.6
inches
0.41
0.08
2.36
1.58
1.41
1.87
Figure 37 depicts the irrigation, precipitation, and runoff versus
time data for Cycle II, and similar data for Cycle III are presented
in Figure 38. During the June-July cycle (Cycle III) there was no
runoff for application amounts of 1 and 2 inches, but the percentage
of runoff increased as the amount of irrigation increased from 3
through 6 inches. This indicates that as the soil profile filled with
water, percolation rate within the soil profile was controlling runoff
from the watershed. Also, it should be noted in Figure 38 that runoff
decreased sharply immediately after the termination of irrigation but
persisted for another 12 to 24 hours in a hydrograph pattern which is
typical for interflow.
The runoff hydrographs for the March-April cycle, shown in Figure 37,
are not as uniform as those for the June-July cycle. The runoff peaks
do not always occur simultaneously with the termination of irrigation
and the peaks are not always followed by rapidly declining recession
curves. These non-uniformities were due primarily to the temperature
changing from above to below freezing and vice versa. These temper-
ature changes controlled the amounts of water being stored as ice or
released from ice on the watershed.
The height of water rise inside a piezometer indicates the water
pressure at its base. Piezometers therefore monitor changes in hy-
draulic pressure of water in the soil pores. Typical pressure head
86
-------
oo
Irrigation KVVsNM
Precipitation
»**•
o.
•H
1
1
a>
4J
0.2
0.1
0
E
a
60
- • 100 •
I
*w
o
- § 50 -
0
^•(^••^•••^••^•••JM
I
0
6 8 10
Time—days after Start of Cycle
12
14
"a0'2
-H
I
5 °-1
0
150
I
60
• : 100
O
I 5°
1
1
19 20 21 22
24 26 28 30
Time—days after Start of Cycle
32
34
36
Figure 37. Irrigation, Precipitation and Interflow Runoff at Various Times After Start of
Cycle II, Mar. - Apr., 1967.
-------
.C
cu
0.4
0.3
0.2
0.1
0
Irrigation KSXNV<|
Rainfall
0
4 6 8 10
Time—days after Staft of Cycle
12
14
16
18
oo
ao
0.4
0.3
o,
•H
! 0.2
a>
0.1
0
15
oo
i
h •iioo
SO'
Oi
Runoff
19 20 22 24 26 28 30
Time—days after Start of Cycle
32
,327
34
36
Figure 38. Irrigation, Precipitation and Interflow Runoff at Various Times After Start of
Cycle III, June - July, 1967.
-------
versus time response patterns for all piezometers are shown in
Figure 39. Throughout all cycles the same 15 piezometers continued
to respond while 10 piezometers did not respond, as indicated by
the nearly horizontal lines in Figure 39.
Piezometer response to irrigation was affected by textural stratifi-
cation of the soil profile. Piezometers which terminated in clay
layers showed little pressure head response to irrigation. Those
which terminated in sandy layers respond rapidly, and at some sites
artesian effects were noted.
Table 24 is based on the highest recorded pressure heads for each
cycle and run, considering only those piezometers which showed
marked response to irrigation. The data indicate that the piezometer
peak pressure heads averaged over all five piezometer depths were
the highest during Cycle II and the lowest during Cycle III. Corres-
pondingly the greatest average percent runoff occurred in Cycle II.
Table 24. Average Peak Pressure Heads in Piezometers for the Six
Runs and the Three Cycles
Cycle I Cycle II Cycle III
Run (Oct-Nov) (Mar-Apr) (June-July)
Pressure Head Pressure Head Pressure Head
1
2
3
4
5
6
ft
1.07
2.64
2.97
3.24
3.52
3.42
ft
2.44
3.51
3.73
3.69
3.77
3.74
ft
0.55
0.94
2.81
3.20
3.41
3.66
The 1968-69 Runoff Investigation
Site Description and Procedures. This study on the same Hublersburg
soil site used by Myers [14) was conducted to determine the difference
between the watershed's responses with respect to runoff peak rates,
total runoff volumes, and chemical quality of the runoff under two
irrigation procedures. The one irrigation procedure applied effluent
to the entire watershed simultaneously to maximize its hydrologic
response, while the second procedure applied effluent during a
sequence of times to minimize its hydrologic response.
Twenty-one sprinklers on four irrigation lines covering the watershed,
lines Ag 7, 8, 9, and 10, were run simultaneously for the maximum
89
-------
to
O
Sta. 5
r\
*x \
it V\
Sta. 4
Sta. 3
U-l
I
I
•O
\\
\\
o'
0 40 80 120 160
Hrs. after Start of Irrig.
Sta. 2
0 40 80 120 160
Hrs. after Start of Irrig.
0 40 80 120 160
Hrs. after Start of Irrig.
0 40 80 120 160
Hrs. after Start of Trrig.
0 40 80 120 160
Hrs. a-fter. Start of Irrig.
2-foot Depth
4-foot Depth
6-foot Depth
8-foot Depth
10-foot Depth
Figure 39. Piezometer Heads (P/W) vs. Hours After Start of 3-inch Irrigation for All Stations
and Depths During Cycle I, Oct., 1966.
-------
procedure, whereas during a typical minimum procedure line Ag 9 with
seven sprinklers was run on Monday, Ag 7 and 10 with a total of 15
sprinklers were run on Wednesday, and Ag 8 with 8 sprinklers was run
on Friday. Each run was for an eight-hour period and applied the
equivalent of two inches of effluent. Each application procedure
was referred to as a sequence and either a minimum or maximum sequence
was run in any one week. A series of sequences run during a particu-
lar climatic period was a cycle. A cycle consisted of a minimum and
maximum sequence each preceded by a preliminary sequence designed to
establish appropriate hydrologic conditions. The sequence, areas
irrigated, and dates of each of the five cycles composing this study
are listed in Table 25.
In addition to securing piezometer, shallow well, and runoff data,
soil temperature was measured at the locations at depths of 0, 3, 6,
12 and 18 inches with thermistor probes installed in place. Runoff
data were recorded continuously but other data were taken at the time
irrigation started, runoff started, irrigation stopped, and runoff
stopped.
Hydrologic Measurements. Figure 40 presents typical irrigation
precipitation, and runoff data plotted against time. These data are
for Cycle III run during February-March of 1969. Table 26 lists the
percentage of effluent volume applied which appeared as runoff during
the minimum and maximum sequences for the five irrigation cycles.
Cycle I and IV are typical of early fall and late spring irrigations,
where greater percentages of water run from the area and higher peak
rates of runoff occurred during the maximum sequence than during the
minimum sequence. Cycles II and III, run during periods when soil
frost essentially stopped infiltration and the surface was coated with
ice, gave more runoff and higher peak rates of runoff during the min-
imum sequence because more of the applied effluent was stored on the
landscape as ice during the maximum sequence. Cycle V is typical of
irrigating during the growing season where no runoff occurred due to
the irrigation.
Peak runoff rates relative to irrigation application rates for the
five cycles are given in Table 27. Cycles I and IV are again what
one would expect, where greater peaks occur from the maximum sequences
than from the minimum sequences. The minimum sequences of Cycles II
and III, however, produced greater peak flow than the maximum sequences.
The maximum air temperature data during these cycles, listed in Table
28, help explain this atypical response. It so happened that during
the maximum sequences it was sufficiently cold to form ice which was
retained on the watershed, while during the minimum sequences the
applied water was not immobilized as ice and it was warm enough to
melt some of the previously stored ice.
91
-------
Jsi
Line Run
0.0
A
P.
•H
1 0.5
0)
150
6
l.OL glOO
i
i
M-l
U-l
0 50
i
o
1/30
Line Run
0.0
2/23
All
Precipitation
Runoff
Irrigation
2/1
2/3 2/5 2/7
Dates of Cycle
2/9
7&10
7&10
2/25
2/27
3/1 3/3
Dates of Cycle
3/5
All
j /
2/11 ' '2/13
3/7
Figure 40. Irrigation, Precipitation and Runoff During Cycle III, Feb. - Mar., 1969.
-------
Table 25. Sequences, Areas Irrigated and Dates of Each Irrigation
Cycle
Cycle
I
II
III
IV
V
Sequence
Pre-Min
Minimum
Pre-Max
Maximum
Pre-Min
Minimum
Pre-Max
Maximum
Pre-Max
Maximum
Pre-Min
Minimum
Pre-Max
Maximum
Minimum
Pre-Max
Maximum
Pre-Min
Minimum
Area Irrigated
Mon Tues Wed Thur
9a 7§10
9 , 7§10
Allb
All
9 7§10
9 7§10
All
All
All
All
9 7§10
9 7§10
All
All
9 7(110
All
All
9 7§10
9 7§10
Fri
8
8
8
8
8
8
8
8
8
Week
beginning
11/18/68
11/25/68
12/2/68
12/3/68
1/6/69
1/13/69
1/20/69
1/27/69
2/3/69
2/10/69
2/24/69
3/3/69
3/24/69
3/31/69
4/7/69
5/26/69
6/2/69
6/23/69
6/30/69
aNumbers given under "Area Irrigated" indicate the irrigation lines
in the Agronomic Area which ran that day.
b"All" indicates the maximum sequence with lines Ag 7, 8, 9 and 10
irrigating simultaneously.
93
-------
Table 26. Percentage of Effluent Volume Applied Appearing as Runoff
during the Minimum and Maximum Sequences for Five
Irrigation Cycles
Cycle
Minimum Sequence
Maximum Sequence
I
II
III
IV
V
23
55
84
11
0
27
34
56
20
0
Table 27. Peak Runoff Rates Relative to Irrigation Application Rates
during the Minimum and Maximum Sequences for the Five
Irrigation Cycles
Irrigation Cycle
Irrigation
Sequence
Maximum
Minimum
Minimum
Minimum
Minimuma
• Area
Irrigated
Ag 7, 8, 9 § 10
Ag 9
Ag 7 § 10
Ag 8
Ag 7, 8, 9 § 10
I
%
43
48
24
36
36
II
1
52
108
88
41
79
III
%
76
211
85
83
126
IV
%
36
37
6
18
20
V
\
0
0
0
0
0
Values given in this row are the peak runoff rates for the entire
watershed obtained by averaging the peak runoff rates for the indi-
vidual runs (Ag 9, Ag 7 § 10 and Ag 8) during the minimum sequences.
94
-------
Table 28. Maximum Air Temperatures and Peak Rates of Runoff Relative
to Irrigation Application Rates lor Cycles II and III
Cycle Sequence
Area
Irrigated
Air Temperature
During Irrigation
Period
Relative
Rate
of Runoff
OT
percent
I
II
III
Minimum
Maximum
Minimum
Maximum
Maximum
Minimum
Ag 9
Ag 7 § 10
Ag 8
All
Ag 9
Ag 7 § 10
Ag 8
Alia
All
Ag 9
Ag 7 § 10
Ag 8
Max
42
44
45
25
34
34
33
28
33
40
35
32
Min
25
40
38
5
27
22
32
8
19
26
19
28
48
24
36
43
108
88
41
52
76
211
85
83
" indicates that lines Ag 7, 8, 9 and 10 irrigated simultaneously.
Runoff Water Quality Measurements. Phosphorus and nitrogen content of
the applied effluent and of the runoff for the five cycles are given
in TaHe 29. The concentrations of the^e two elements were smaller in
the runoff samples than in the applied effluent for Cycles I and IV
during which time the effluent could infiltrate and percolate through
the upper soil layer. During Cycles II and III, a concrete soil frost
diminished infiltration and the nutrient level of the runoff frequent-
ly was higher than in the applied effluent due to "freeze concentra-
tion" of the impurities as pure water was frozen out.
Results from this study, thus indicate that during periods when
infiltration and percolation rates are not decreased by soil frost,
sequencing the application of effluent irrigation is advantageous.
During periods when soil frost essentially prevented infiltration and
the surface was coated with ice, however, sequencing had no beneficial
effect on total runoff but did result in a generally lower content of
phosphorus and nitrogen in the runoff. If samples of runoff during
irrigation with lines 7, 8 and 10 in the minimum sequence had been
averaged with that from line 9 concentration of both phosphorus and
nitrogen would have been even lower in the minimum sequence.
95
-------
.Table 29. Concentrations in Parts Per Million of Phosphorus and Nitrogen and Percent Change in
Concentration in Watershed Runoff at Four Sampling Times for Four Irrigation Cycles
PHOSPHORUS
Minimum Sequence
Irrigation Cycle
Sampling Times
I
P
0,
*0
Change
ppm
.Applied Effluent
Runoff Started
Irrigation Stopped
Runoff Stopped
Ave
11
7
6
4
rage
.75
.00
.88
.62
-40
-41
-60
-47
P
II
9.
•6
Change
ppm
10.
13.
10.
10.
00
75
00
82
+37.5
0
+8
+15
III
P
ppm
6.12
5.25
3.50
3.38
9.
a
Change
-14
-43
-45
-34
IV
P
ppm
7.50
1.62
1.38
0.70
o.
0
Change
-78
-82
-90
-83
Average
«.
1)
Change
-37
Sampling Times
Maximum Sequence
Change
Irrigation Cycle
II III
IV
Change
Change
Change
ppm
Applied Effluent
Runoff Started
Irrigation Stopped
Runoff Stopped
10.
12.
13.
13.
Average
12
50
00
75
+24
+28
+36
+29
ppm
5.80
6.05
5.45
7.65
ppm
+4
-6
+32
+10
7.
9.
5.
5.
50
68
50
68
+29
-27
-32
-10
ppm
7.25
4.25
4.15
1.62
-41
-43
-77
-54
-6
-------
Table 29. (continued).
TOTAL NITROGEN (includes
Minimum Sequence3
Sampling Times
Applied Effluent
Runoff Started
Irrigation Stopped
Runoff Stopped
Average
I
N
Ppm
30.10
19.40
24.20
Maximum
organic N, NH,
Irrigation
II
%0.
Change
-16
-20
Sequence
N
ppm
42.70
48.00
42.30
43.04
t>
Change
+12
- 1
+ 1
+ 4
-N and No-j-N)
Cycle
III
0.
N
ppm
33.50
33.54
26.02
29.04
Irrigation
Sampling Times
Applied Effluent
Runoff Started
Irrigation Stopped
Runoff Stopped
Average
I
N
ppm
20.50
26.70
24.00
31.90
Change
+30
+17
+56
+37
N
ppm
32.66
35.40
37.24
44.84
II
Change
+ 8
+14
+37
+20
•6
Change
0
-22
-13
- 9
Cycle
III
&
N
ppm
35.40
53.56
30.26
33.76
"0
Change
+52
-15
- 5
+11
rv
N
ppm
31.00
8.50
10.30
IV
N
ppm
27.20
21.70
22.90
16.30
0.
%
Change
-73
-67
Change
-20
-16
-40
-25
Average
Change
+10
Values listed for the minimum sequences are those concentrations secured from samples taken on the
day line Ag 9 ran.
-------
SECTION VI
CROPLAND ASPECTS
Effect of Effluent on Agronomic Crops
Previous Studies. The effect of sewage effluent on the yield of
agronomic crops has generally been found to be a beneficial one.
Henry e_t al. (24) obtained a significant increase in the yield of reed
canarygrass. The authors concluded that nutrients such as nitrogen,
phosphorus and potassium were being removed by the crop since there
was little in the percolate. A similar conclusion was made by
Heukelekian (25).
Irrigating by canals and ditches, Stokes et al. (26) obtained yield
increases amounting to 240 percent for botn" Napier grass and Japanese
cane when compared with the unirrigated crops. He states that yields
from plots irrigated with well water were not significantly higher
than the unirrigated plots and concluded that the difference was due
to nutrients supplied in the effluent. In the effluent the nitrate
concentration was zero ppm but free ammonia was 27.3 ppm and P20s
8.2 ppm Day and Tucker (27, 28) applied three acre-feet of sewage
effluent containing a total of 195 pounds of nitrogen, 150 pounds of
phosphoric acid and 96 pounds of potash to plots on which barley,
wheat and oats were grown for hay. Compared with crops irrigated
with well water only, the effluent-irrigated crops increased in yield
by 112 percent for barley, 263 percent for wheat and 249 percent for
oats. When commercial fertilizers were added to the well water and
the effect compared with that of sewage effluent, barley yielded 22
percent less when irrigated with the effluent but wheat and oats
yielded more. This was believed to indicate a sensitivity of barely
to sewage effluent. The lower yield of barley was attributed to its
greater sensitivity to the presence of detergents in the effluent and
to the higher accumulation of soluble salts in the effluent-irrigated
plots. The yields of grain produced in the same experiment were
reported by Day e_t al. (29). Compared with plots irrigated with well
water without fertilizer, those irrigated with sewage effluent gave
increases of 190 percent for barley, 163 percent for oats and 200
percent for wheat. Grain yields with well water and fertilizer equiv-
alent to the N, P205 and K20 in the sewage effluent were 300-400 Ibs
per acre less than with the sewage effluent. The only unfavorable
feature of the effluent irrigated plots was the lodging that occurred.
It was evident however that small grain crops could utilize nitrogen
from sewage effluent as efficiently as from commercial fertilizers.
Using papermill waste, Vercher et al. (30) obtained a significant
increase in the yield of corn compared with the unirrigated crop.
However, there was no significant difference between the yields from
99
-------
plots irrigated with well water or waste water. Neither oats nor
cowpeas showed a significant difference in yield between treatments.
Site Description and Procedures. The agronomic crops were grown on
a site which had been producing hay, small grain, and corn for many
years and had been receiving normal amounts of lime, manure and
fertilizer. The area selected for the wastewater research, designated
in Table 3 as Agronomy Area (A), was located on a Hublersburg soil
with a surface texture ranging from silt loam to clay loam to silty
clay loam to clay. The area ranged in slope from 31 to 161 and aver-
aged about 4%. The strip-crop area was divided into three adjacent
plots, each 800 feet long and 240 feet wide (4.4 acres each) as shown
in Figure 41. The crops were grown in seven strips across the slope
in a rotation sequence as indicated in Table 30.
The control plot (A-0) received commercial fertilizer in amounts
normally recommended for the individual crops but received no irriga-
tion. The irrigated plots (A-l and A-2) received no commercial
fertilizer. The reed canarygrass area (A-3), occupying 16 acres
adjacent to the rotation area, was seeded in 1964, has been irrigated
with wastewater year-round since then, and has received no commercial
fertilizer. The irrigation systems and programs for these three areas
are given in Table 3 and Table 31.
Crop response was measured in terms of yields and chemical quality.
Forage harvests were made two or three times per year by mowing and
weighing six strips, each 30 feet by 3 feet, in each rotation strip
and in the reed canarygrass area. Subsamples were taken for deter-
mination of dry matter and subsequently ground in a Wiley mill in
preparation for chemical analysis.
Corn grain yield was determined by removing and weighing ears along
six randomly selected 30-foot rows in each rotation strip. Subsamples
of kernels were removed from each ear and composited for determination
of moisture by a dielectric method and grain yield converted to 15.5%
moisture basis. After oven drying the grain was ground for chemical
analysis.
Corn stover or silage was cut by hand from six randomly selected 30-
foot rows in each rotation strip and weighed in the field. Three
representative stalks were selected from each lot, weighed, then oven
dried to determine dry matter content. These subsamples were ground
in a hammer mill and then a sub-subsample ground in a Wiley mill in
preparation for chemical analysis.
Yield of the only wheat harvest was measured by combining six strips,
each 87 feet long x 10 feet wide in each rotation strip and weighing
the bagged grain. Oats were hand cut with a sickle from randomly
100
-------
N
A-0
O
O
00
\/
240 ft
A-l
A-2
I
2
3
scale I in. = 200 ft
Figure 41. Plan of Strip Cropped Area.
101
-------
Table 30. Crop Rotation Sequence
Strip Nunber
1
2
3
4
5
6
7
1963
corn
wheat
red clover
wheat
corn
red clover
alfalfa
1964
oats
red clover
corn
red clover
oats
corn
corn
1965
alfalfa
corn
oats
com
alfalfa
oats
oats
1966
alfalfa
corn
alfalfa
corn
alfalfa
alfalfa
alfalfa
1967
alfalfa
corn
alfalfa
corn
alfalfa
alfalfa
alfalfa
1968
corn
corn
corn
corn
com
corn
corn
1969
corn
corn
corn
com
corn
corn
corn
-------
Table 31. Irrigation Program for Agronomy Areas
Seasonal Irrigation Amounts - inches
Weekly _ __
Application I9l>3155? 1933 1535 I9"6"719l>E19l>9"
Area No. Inches June-Dec Mar-Nov Apr-Nov Apr-Nov Apr-Nov May-Sept May-Sept Total
A-l
A- 2
1
2
24
48
33
66
29
58
32
64
26
52
20
40
16
32
180
360
July-Nov Apr-Dec Jan-Dec Jan-Dec Jan-Dec Jan-Dec
A-3 2 36 80 78 94 98 100 486
-------
selected sub-plots, 30-feet by 3.5 feet, in each rotation strip. The
oats were threshed in a small head thresher and grain and straw yields
determined from the separate weights. Subsamples of grain and straw
were ground in preparation for chemical analysis. The methods used
in chemically analyzing the plant materials are given in the appendix.
Crop Yields. The crop yields and percentage differences in yield due
to sewage effluent application are given in Tables 32 through 38.
With the exception of the wheat crop in 1963 which essentially had
made its growth before irrigation began on June 19, and the oat crops
in 1964 and 1965>increases in yield due to irrigation with the waste-
water were highly significant (P=.01) for all rotation crops in 1963,
1964, 1965, and 1966. The oat yield differences were large but lodging
caused a high degree of variation from sub-plot to sub-plot and hence
diminished its statistical reliability. Rainfall in the growing
season of years 1963-1966 was substantially below normal, as shown in
Table 39, hence the favorable^ response was in part due to the added
water on the irrigated plots. In most cases the 2-inch per week treat-
ment was not significantly different from the 1-inch. Exceptions
where the 2-inch treatment out yielded the 1-inch occurred with alfalfa
in 1965, 1966 and 1967 and with both corn grain and silage in 1966.
During the more moist growing seasons of 1967, 1968 and 1969 yield
response to irrigation with wastewater was less dramatic but did occur
with grain corn (Pa. 444 in 19-inch rows) and alfalfa in 1967. In 1968
only corn was grown on the rotation strips. An attempt to control
weeds with 2-4D rather than atrazine failed and the corn crop was
smothered in weeds. Hence no yield measurements were made. In 1969
yield differences due to irrigation treatment were not significant.
The control plot had plenty of fertilizer and water to make a good
yield.
The 2-inch irrigated reed canarygrass yields were slightly greater than
the 2-inch irrigated alfalfa and red clover hay yields. Although a
reed canarygrass control area was not available for comparison the
growth of reed canarygrass on unirrigated, unfertilized edges of the
area was substantially less. In 1972, yield from an unirrigated, un-
fertilized plot was only 40% of that from the 2-inch irrigated area.
Crop Composition and Quantities of Nutrients Removed. Nutrients taken
up by the growing crops from the applied wastewater should result in
its renovation. To the extent that the nutrients are removed as
harvested crops and recycled through man's food chain, the crops are
a very important component of the "living filter" system of wastewater
renovation.
A close examination of the nutrient content of the rotation crops in
Tables 40 through 48 and Appendix Tables 1-6 indicates that, out of 64
crop-treatment cases cited, effluent irrigated crops contained more
104
-------
Table 32. Crop Yields and Percentage Increase in Yields at Various Levels of Sewage Effluent
.Application - 1963
o
tn
0 Inch Per Week
1 Inch Per Week
2 Inches Per Week
Crop
Corn Grain (bu/a)*
Corn Stover (t/a)***
Wheat Grain (bu/a)
Red Clover 1st cut (t/a)****
Red Clover 2nd cut (t/a)****
Red Clover total (t/a)****
Alfalfa 1st cut (t/a)****
Alfalfa 2nd cut (t/a)****
Alfalfa total (t/a)****
Yield
75. Oa**
4.3a
48. Oa
1.61a
0.87a
2.48a
1.48a
0.70a
2.18a
Yield
105. 4b
6.7b
44. 9a
2.70b
2.20b
4.90b
1.89a
1.84b
3.73b
% Increase
41
55
-6
68
153
98
28
163
71
Yield
106. Ib
6.8b
53. 5a
2.14b
2.45b
4.59b
2.76b
2.36c
5.12c
% Increase
41
58
13
33
182
85
86
237
135
*Bushels per acre, corrected to 15.5 percent moisture basis.
**Values in the same row not having a common letter were highly significantly different (P-0.01)
The same designation also applies to Tables 33, 34, 35, 36, 37 and 38.
***Tons per acre, field moisture basis.
****Tons per acre, dry matter basis.
-------
Table 33. Crop Yields and Percentage Increase in Yields at Various Levels of Sewage Effluent
Application - 1964
Crop
Corn Grain (bu/a)*
Corn Stover (t/a)**
Oats Grain (bu/a)
Red Clover 1st cut (t/a)***
Red Clover 2nd cut (t/a)***
Red Clover total (t/a)***
0 Inch Per Week
Yield
80. 7a
3.83a
82. 4a
1.48a
0.28a
1.76a
1 Inch
Yield
120. 9b
7.29b
124. 5a
3.38b
1.92b
5.30b
Per Week
1 Increase
50
90
51
128
586
201
2 Inches Per Week
Yield % Increase
116. Ib 44
8.48b 121
97. Oa 18
3.22b 118
1.90b 578
5.12b 191
*Bushels per acre, corrected to 15.5 percent moisture basis.
**Tons per acre, field moisture basis.
***Tons per acre, dry matter basis.
-------
Table 34. Crop Yields and Percentage Increase in Yields at Various Levels of Sewage Effluent
Application - 1965
Crop
Corn Grain (bu/a)*
Com Silage (t/a)**
Oats Grain (bu/a)
Oats Straw (t/a)**
Alfalfa 1st cut (t/a)**
Alfalfa 2nd cut (t/a)**
Alfalfa 3rd cut (t/a)**
Alfalfa total (t/a)**
0 Inch Per Week
Yield
63. 3a
3.11a
44. 9a
1.62a
1.63a
O.OSa
0.59a
2.27a
1 Inch
Yield
114. 4b
3.93b
80. 5a
2.90a
2.72b
0.89b
1.06b
4.67b
Per Week
1 Increase
81
26
79
79
67
1680
80
106
2 Inches
Yield
110. 8b
4.32b
72. 5a
2.63a
2.93b
1.38c
l.llb
5.42b
Per Week
% Increase
75
39
61
62
80
2660
88
139
*Bushels per acre, corrected to 15.5 percent moisture basis.
**Tons per acre, dry matter basis.
-------
CD
CO
Table 35. Crop Yields and Percentage Increase in Yields at Various Levels of Sewage Effluent
Application - 1966
Crop
Corn Grain (bu/a)*
Corn Silage (t/a)**
Alfalfa 1st cut (t/a)**
Alfalfa 2nd cut (t/a)**
Alfalfa 3rd cut (t/a)**
Alfalfa total (t/a)**
0 Inch Per Week
Yield
33. 4a
2.47a
1.48a
0.33a
0.14a
1.9Sa
1 Inch
Yield
98. 4b
4.45b
2.17b
1.13b
0.56b
3.86b
Per Week
1 Increase
295
80
57
242
300
98
2 Inches
Yield
115. 5c
5.68c
2. lib
1.54c
0.73c
4.38c
Per Week
\ Increase
346
130
42
367
421
125
*Bushels per acre, corrected to 15.5 percent moisture basis.
**Tons per acre, dry matter basis.
-------
Table 36. Crop Yields and Percentage Increase in Yields at Various Levels of Sewage Effluent
Application - 1967
Crop
Corn Grain Pa. 444
19 inch row (bu/a)*
38 inch row (bu/a)*
Corn Pa. 602 -A
Grain 19 inch row (bu/a)*
Silage 19 inch row (t/a)**
Alfalfa 1st cut (t/a)**
Alfalfa 2nd cut (t/a)**
Alfalfa total (t/a)**
0 Inch Per Week
Yield
97. 9a
91. 6a
122. 2a
4.43a
1.35a
l.OSb
2.43a
1 Inch
Yield
101. lab
83. Oa
120. 9a
4.47a
2.87b
0.90a
3.77b
Per Week
% Increase
3
-9
-1
<1
113
-17
55
2 Inches
Yield %
121. 7b
84. 5a
113. 5a
4.67a
2.99b
1.37c
4.36c
Per Week
Increase
24
-8
-7
5
115
40
76
*Bushels per acre, corrected to 15.5 percent moisture basis.
**Tons per acre, dry matter basis.
-------
Table 37. Crop Yields and Percentage Increase in Yields at Various Levels of Sewage Effluent
.Application - 1969
Crop
Corn
0 Inch
Per Week
Yield
1 Inch
Yield
Per Week
% Increase
2 Inches
Yield
Per Week
% Increase
Silage
Pa.
Pa.
890- S (t/a)*
602 -A (t/a)*
6.
5.
90a
19a
6.
5.
66a
77a
-3
11
7
5
.27a
.49a
5
6
*Tons per acre, dry matter basis.
-------
Table 38. Yields* of Reed Canarygrass Receiving Two Inches of
Sewage Effluent Per Week - 1965-1969
Year
1st Cut
2nd Cut
3rd Cut
Total Yields
1965
1966
1967
1968
1969
2.77
2.57
3.77
3.00
2.83
2.39
1.37
1.88
2.09
1.71
0.97
0.38
1.38
-
0.64
6.13
4.32
7.03
5.09
5.18
Tons per acre, dry matter basis.
Table 39. Normal Monthly Precipitation and Deviations from the Normal
Inches
May
June
July
Aug
Sept
Seasonal
Deviation
Normal
1963
1964
1965
1966
1967
1968
1969
4.00
-1.07
-3.49
-1.57
-0.86
+0.57
+1.98
-1.79
3.35
-1.09
-0.31
-2.10
-3.12
-1.87
+0.10
+0.05
3.53
+0.28
-0.84
-2.29
+0.58
+4.05
-1.92
+2.65
3.43
-0.93
+0.06
+0.32
-2.51
+0.80
-0.06
+0.68
2.60
-0.20
-1.47
+0.33
+2.45
+1.29
+1.05
-0.80
-3.23
-6.05
-5.31
-3.46
+4.84
+1.15
+0.79
111
-------
Table 40. Average Nutrient Composition of Red Clover Hay Receiving
Various Levels of Sewage Effluent Per Week. 1963-1964
Nutrient
Crop
0
Year and
1963
1
Inches
2
of Effluent
0
Applied
1964
1
Per Week
2
Percent
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
1.
0.
2.
1.
0.
86
217
08
060
162
-
2.
0.
2.
1.
0.
21
266
69
296
227
-
2
0
2
1
0
.29
.266
.65
.298
.236
-
2
0
1
0
0
0
.03
.191
.90
.672
.140
.40
2.72
0.326
3.06
0.948
0.315
1.06
2
0
2
0
0
1
.38
.294
.79
.653
.233
.25
Micrograms per grams
Boron - - - 15 26 15
112
-------
Table 41. Average Nutrient Composition of Alfalfa Hay Receiving Various Levels of Sewage
Effluent Per Week. 1963, 1965-1967
Nutrient
0
1963
1
Crop Year
2
0
and Inches of
1965
1
2
Effluent
0
Applied Per Week
1966 1967
1
2
0 1
2
Percent
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
1.75
0.245
1.95
0.646
0.122
-
1.92
0.308
2.25
0.670
0.152
-
1.87
0.313
2.28
0.442
0.141
-
2.12
0.185
2.04
0.980
0.132
0.53
2.66
0.293
2.55
0.647
0.216
1.16
2.62
0.312
2.75
0.660
0.225
1.23
2.91
0.244
2.48
1.03
0.15
0.55
2.35
0.327
2.83
0.66
0.20
1.07
Micrograms per
Sodium
Boron
-
_
-
_
-
_
14
_
16
_
19
_
23
17
224
14
2.14
0.330
2.78
0.54
0.19
1.22
gram
197
10
1.82 1.54
0.26 0.28
2.21 2.39
0.95 0.43
0.15 0.14
0.62 1.04
31 154
17 9
2.10
0.30
2.53
0.39-
0.16
1.18
157
8
-------
Table 42. Average Nutrient Composition of Crops Receiving Various Levels of Sewage Effluent
Per Week - 1963
Crop and Inches of Effluent Applied
Corn Grain
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
0
1.79
0.426
0.37
0.008
0.143
1
1.69
0.382
0.32
0.005
0.108
2
1.70
0.446
0.47
0.005
0.129
Wheat Grain
0
1.99
0.504
0.47
0.050
0.130
1
Percent
2.37
0.599
0.43
0.050
0.149
2
2.58
0.636
0.37
0.055
0.165
Per Week
Wheat Straw
0
0.73
0.008
0.99
0.260
0.072
1
0.84
0.118
0.96
0.303
0.096
2
0.92
0.155
1.09
0.277
0.082
-------
On
Table 43. Average Nutrient Composition of Crops Receiving Various Levels of Sewage Effluent
Per Week - 1964
Crops and Inches
Corn Grain
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
0
T.90
0.187
0.34
0.050
0.077
0.06
1
1.36
0.163
0.35
0.050
0.068
0.04
2
1.74
0.166
0.35
0.050
0.066
0.04
of Effluent Applied Per Week
Corn Stover
0
0.63
0.076
1.25
0.480
0.168
0.38
1
Percent
0.55
0.061
1.36
0.370
0.185
0.72
Micrograms per
2
0.70
0.158
1.40
0.330
0.160
0.60
gram
0
1.64
0.372
0.73
0.140
0.145
0.16
Oat Grain
1
1.07
0.465
0.67
0.120
0.145
0.11
2
1.86
0.477
0.64
0.130
0.153
0.07
Boron
10 11 10
-------
Table 44. Average Nutrient Composition of Crops Receiving Various Levels of Sewage Effluent
Per Week - 1965
Nutrient
Corn Grain
0 1
Crop and Inches of Effluent Applied Per Week
Corn Silage Oat Grain
Oat Straw
0
0
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Boron
1.78 1.75 1.81
0.545 0.611 0.653
0.57 0.60 0.63
0.012 0.021 0.059
0.208 0.203 0.229
0.03 0.04 0.06
Percent
1.45 1.36 1.29
0.176 0.217 0.223
1.12 1.01 1.18
0.550 0.420 0.370
0.171 0.221 0.190
0.25 0.37 0.38
2.03 1.99 1.55
0.353 0.448 0.423
0.83 0.57 0.56
0.157 0.105 0.103
0.137 0.142 0.139
0.22 0.09 0.09
Micrograms per\gram
57 54
0.43 0.29 1.12
0.047 0.114 0.135
2.48 1.94 1.86
0.740 0.420 0.430
0.136 0.150 0.106
1.35 1.03 1.50
-------
Table 45. Average Nutrient Composition of Crops Receiving Various Levels of Sewage Effluent
Per Week - 1966
Crop and Inches of Effluent Applied Per Week
Corn Silage Corn Grain
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Sodium
Boron
0
1.90
0.246
1.05
0.42
0.18
0.33
13
5
1
1.42
0.311
1.07
0.31
0.20
0.40
250
5
2
Percent
1.25
0.340
1.16
0.28
0.20
0.39
Micrograms per
211
5
0
2.51
0.453
0.38
*
0.17
0.04
gram
5
*
1
1.96
0.507
0.44
*
0.17
0.05
5
*
2
1.95
0.614
0.45
ft
0.17
0.07
8
*
Less than 0.10% Ca and less than 5 micrograms B per gram.
-------
oo
Table 46. Average Nutrient Composition of Crops Receiving Various Levels of Sewage Effluent
Per Week - 1967
Crop and Inches of Effluent Applied Per Week
Corn Grain Pa. 444 Corn Pa. 602 -A*
19" Row Spacing
Nutrient
0
1
2
38" Row Spacing
0
1
2
0
Grain
1
2
Silage
0 1
2
Percent
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
1.48
0.35
0.33
**
0.12
0.07
1.61
0.45
0.37
**
0.14
0.06
1.50
0.47
0.36
**
0.14
0.02
1.81
0.45
0.40
**
0.14
0.04
1.63
0.51
0.39
**
0.16
0.05
1.82
0.51
0.40
**
0.16
0.02
Micrograms
Sodium
Boron
12
2
13
2
5
3
25
2
6
3
4
3
1.68
0.38
0.37
A*
0.13
0.05
1.63
0.45
0.43
**
0.13
0.06
1.64
0.52
0.44
**
0.14
0.02
1.00 1.06
0.18 0.25
1.23 1.23
0.28 0.24
0.14 0.18
0.32 0.38
1.18
0.32
1.36
0.21
0.19
0.39
per gram
16
2
18
3
9
2
22 160
4 6
188
7
^Nineteen inch row spacing.
**Average composition was less than 0.10 percent calcium for grain samples.
-------
Table 47. Average Nutrient Composition of Crops Receiving Various Levels of Sewage Effluent
Per Week - 1969
Crop and
Corn Silage Pa,
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Sodium
Boron
0
1.83
0.19
0.88
0.24
0.13
0.27
26
4
1
1.67
0.26
0.89
0.21
0.17
0.36
112
4
Inches of Effluent Applied Per Week
. 890 -S Corn Silage Pa. 602 -A
2
Percent
1.63
0.30
1.03
0.19
0.17
0.37
Micrograms per
123
5
0
1.63
0.23
1.13
0.34
0.14
0.34
gram
10
7
1
2.16
0.26
1.27
0.25
0.20
0.42
163
7
2
1.80
Oi32
1.16
0.15
0.16
0.32
165
'S
-------
Table 48. Average Nutrient Composition of Reed Canary-grass Receiving
Two Inches of Sewage Effluent Per Week. 1965-1969
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
1965
3.00
0.33
2.63
0.54
0.25
1.56
1966
3.15
0.39
2.90
0.33
0.22
1.41
Years
1967
Percent
2.34
0.40
2.44
0.46
0.29
1.44
1968
3.50
0.46
-2.50
0.40
0.28
1.67
1969
3.42
0.45
2.07
0.47
0.35
1.67
Micrograms per gram
Sodium
Boron
408
8
137
6
334
7
304
5
259
11
phosphorus in 92% and more potassium in 78% of the cases. However,
although not as strongly expressed, the effect of effluent irrigation
on nitrogen content was reversed. The fertilized but unirrigated
crops contained more nitrogen in 53% of the cases. Irrigated hay
crops (alfalfa and red clover) were more often higher in nitrogen, 541
of the cases, whereas irrigated corn and small grains were less often
higher in nitrogen, 42% of the cases. Irrigated crops were generally
not higher in calcium, only 18% were higher, or in boron, only 44%
were higher. The latter occurred even though substantial amounts of
boron were added in the applied effluent. However, irrigated crops
were generally higher in magnesium, 80% of the cases, in chloride, 76$
of the cases and sodium, 81% of the cases. Sodium and chloride is
taken up by the plants in much larger amounts and the chloride content
of the alfalfa crops was more than doubled. Although the sodium
content of the crops was much lower than the chloride content its
change in content as a result of irrigation with the wastewater is
greater than,with any other constituent. In alfalfa the sodium
content increased 5 to 10 fold; in silage corn it increased 5 to 15
fold. The significance of these large increases in chloride and sodium
for the nutritive value of these crops for animals is not evident at
this time. Chlorides up to 1500 mg/1 in livestock water has been
reported safe for cattle, sheep, swine and poultry and a threshold
limit of 2000 mgNa/1 for livestock has tentatively been suggested (2).
120
-------
The concentration of nitrogen in the 2-inch irrigated reed Canary-grass
was generally higher than in the alfalfa and red clover hays and
averaged 3.08%. Phosphorus content averaged 0.4%, which exceeded that
of the legume hays and corn silage and was slightly less than that in
corn grain and oats. The average potassium content, 2.51% was slight-
ly less than that in the 2-inch irrigated legume hays (2.63%) and
much greater than in the grains or silage. Data for individual cut-
tings are given in Appendix tables 7 through 11.
Quantities of Nutrients Removed. The quantities of N, P, and K
removed in the harvested crops (Tables 49 to 57) ranged from a low of
29.6 Ib of N/acre for oats on the control area in 1965 to a high of
356 Ib N/A for reed canarygrass in 1968. Corn silage removed sub-
stantially more N and K than corn grain but there was relatively
little difference in the removal of phosphorus by grain and silage.
The mixed legume-grass hay crops were about equally effective as com
grain or silage in removing phosphorus and removed substantially more
potassium; 200 to 300 pounds of K per acre as against 20 to 30 pounds
of K in com grain and 100 to 150 pounds of K in corn silage. Data
for the individual hay cuttings are given in Appendix tables 12-17.
The greatest quantities of all nutrients was removed by the reed
canarygrass. In five years, 1965-1969, it removed from each acre 1665
pounds of N, 224 pounds of P and 1384 pounds of K. The amounts
removed by individual reed canarygrass cuttings is given in Appendix
tables 18-22.
Quantities of Nutrients Applied and Renovation Efficiency of Crops.
The various crops grown all contribute importantly in removing the two
key eutrophic nutrients, P and N, which are being applied in the waste-
water. Their respective renovating efficiencies for these and other
constituents in the wastewater was determined by computing the ratio
of the quantity of the constituent removed in the harvested crop to
the quantity of the constituent added in the applied wastewater. The
latter was computed from the analyses of the applied wastewater shown
in Tables 58 and 59 and the volume of wastewater applied. The quanti-
ties applied annually are shown in Tables 60 and 61 and the computed
renovation efficiencies in Tables 62 through 68.
Variations in composition of the wastewater occurred from year to year
and between the one and two inch applications in any one year. These
are due in part to the variations from year to year in the day of the
week or period in the day when the irrigation occurred. One source of
variation was the detergent industry change in surfactant (MBAS) from
ABS prior to 1965 to LAS after 1965 which resulted in more complete
decomposition of the surfactant in the treatment plant. Prior to 1965,
MBAS averaged 2.69 mg/1; after 1965 it averaged only 0.43 mg/1.
Changes in treatment plant operation and seasonal loads handled by the
plant contributed to some of the variations in the various nitrogen
components. Nitrate concentrations tended to be higher during the
summer months when treatment plant loads were about 40% less than during
121
-------
Table 49. Quantities of Nutrients (Pounds Per Acre) Removed by Red
Clover Receiving Various Levels of Sewage Effluent Per
Week. 1963-1964
Crop Year and Inches of Effluent Applied Per Week
1963 1964
Nutrient 0120
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Boron
91.4
10.8
103.4
52.6
8.0
-
-
216.8
26.0
264.1
127.0
22.3
-
-
210.7
24.4
243.5
119.2
21.7
-
-
71.5
6.8
66.8
23.7
4.9
14.1
0.05
288.5
34.5
324.8
100.4
33.7
112.7
0.28
243.2
29.6
286.4
66.7
23.8
128.4
0.15
the regular academic year because of a reduction in student population
of about 15,000 during the summer period.
Of the various constituents assayed, sodium and chloride were present
in largest quantities and were being added annually in combined totals
of 500 to 1300 Ib/acre in the rotation crop area and 1400 to 2000
Ib/acre in the reed canarygrass area. The three principal fertilizer
nutrients were being added in the 2-inch per week treatment areas at
average annual levels of 47 to 128 IbP/acre, 110 to 248 IbN/acre and
100 to 278 IbK/acre on the rotation crop area; and 95 to 188 IbP/acre,
155 to 525 IbN/acre and 222 to 373 IbK/acre on the reed canarygrass
area. Annual boron additions in the 2-inch treatment ranged from 4.2
to 6.0 IbB/acre in the rotation crop area and from 5.2 to 8.9 IbB/acre
in the reed canarygrass area. The quantities of major plant nutrients
at the low end of the range are about equal to the amounts normally
recommended for the crops grown. The quantities at the upper end of
the range are within the limits which have been used in intensive
management for maximum productivity.
The quantities of boron added annually in both the one- and two-inch
treatments exceed the amounts normally recommended for the crops grown.
However, the normal recommendation of approximately one IbB/acre per
year for alfalfa, which has a high boron need, is usually put on in a
single dose or two doses per season mode and hence results in a higher
short time concentration. If larger amounts were added in a single
application toxic limits would be reached. The wastewater application
122
-------
Table 50. Quantities of Nutrients (pounds per acre) Removed by Alfalfa Receiving Various Levels
of Sewage Effluent Per Week. 1963, 1965-1967
... - T_ __ L { _ __ _
Crop Year
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Sodium
Boron
0
76.1
10.7
85.0
28.2
5.3
-
-
-
1963
1
143.2
23.0
167.9
50.0
11.4
-
-
_
2
191.7
32.0
234.0
45.3
14.5
-
-
_
0
96.5
8.5
92.3
44.6
6.0
24.1
0.07
_
M^WI^M^«IBWV*MMBMV^MI»HI^^AWI^0l«^^tf>VMIM«lmMA*Wl^p*k^B^»BMIv^IIH
and Inches of Effluent
1965
1
248.1
27.6
237.9
60.4
20.2
108.1
0.16
-
2
283.9
33.6
298.0
71.6
24.4
133.3
0.21
_
0
112.4
9.7
95.8
37.7
5.7
21.4
0.12
0.07
.__]I|-T ;. .......1 .. . .... - - . .- . . . — —
Applied Per Week
1966
1
179.6
25.0
219.5
51.9
15.1
83.0
1.81
0.10
2
184.8
28.6
242.1
46.6
16.2
105.5
1.86
0.08
1967
0 1
70.0 114.9
8.6 21.3
74.6 181.1
25.8 31.8
4.6 11.0
20.4 77.5
0.09 1.16
0.04 0.07
2
132.9
24.3
209.0
32.0
12.4
94.8
1.27
0.08
-------
Tabel 51. Quantities of Nutrients (pounds per acre) Removed by Crops Receiving Various Levels
of Sewage Effluent Per Week - 1963
to
Crop and Inches of Effluent Applied Per Week
Corn Grain
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
0
81.4
19.4
16.8
0.3
6.5
1
108.0
24.4
20.6
0.3
6.9
2
109.0
28.7
29.9
0.3
8.3
Wheat Grain
0
57.2
14.5
13.4
1.4
3.7
1
63.8
16.1
11.7
1.3
4.0
2
82.7
20.4
11.9
1.8
5.3
Wheat Straw
0
14.7
1.4
20.1
5.3
1.5
1
9.6
1.3
10.9
3.4
1.1
2
16.0
2.4
19.0
4.8
1.4
-------
Table 52. Quantities of Nutrients (pounds per acre) Removed by Crops Receiving Various Levels-
of Sewage Effluent Per Week - 1964
Cn
Crop and Inches of Effluent Applied Per
Corn Grain
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Boron
0
105.5
10.4
18.8
2.8
4.3
3.2
0.02
1
103.8
14.0
29.5
4.3
5.8,
3.8
0.04
2
141.3
13.6
28.6
4.1
5.4
3.4
0.03
Corn Stover
0
50.6
5.4
94.4
36.4
12.8
11.7
0.04
1
81.2
8.9
197.4
53.5
27.0
32.8
0.05
2
118.5
26.9
237.6
56.0
27.1
30.3
0.05
0
41.8
9.6
19.1
3.8
3.8
4.0
0.01
Week
Oat Grain
1
42.3
18.5
26.6
4.8
5.8
4.5
0.03
2
56.1
14.9
19.9
4.1
4.8
2.1
0.02
-------
Table 53. Quantities of Nutrients (Pounds Per Acre) Removed by Crops Receiving Various Levels
of Sewage Effluent Per Week - 1965
Crop and Inches of Effluent Applied Per Week
Corn Grain
Nutrient
Nitrogen
Phosphorus
Potassiun
Calcium
Magnesium
Chloride
Boron
0
54.6
16.7
17.3
0.4
6.4
2.1
0.01
1
96.9
33.9
33.0
1.2
11.3
2.6
0.02
2
97.2
35.2
33.6
3.2
12.3
1.9
0.02
Corn Silage
0
96.6
11.8
72.8
35.'5
11.2
15.6
0.03
1
107.4
16.9
78.1
32.3
17.4
29.2
0.04
2
110.1
18.9
101.5
31.6
16.4
32.9
0.04
Oat Grain
0
29.6
5.1 .
12.0
2.3
2.0
3.2
0.04
1
51.3
11.4
14.4
2.7
3.6
2.4
0.01
2
35.8
10.0
12.9
2.4
3.2
2.1
0.01
Oat Straw
0
14.4
1.5
100.6
28.8
5.4
43.6
0.02
1
16.9
6.6
112.2.
24.1
6.1
61.6
0.03
2
6.4
7.3
99.7
22.5
5.6
76.6
0.02
-------
Table 54. Quantities of Nutrients (Pounds Per Acre) Removed by Crops Receiving Various Levels
of Sewage Effluent Per Week - 1966
to
Crop and Inches of Effluent Applied
Com Silage
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Sodium
Boron
0
92.3
12.1
51.1
20.4
8.8
16.3
0.06
0.02
1
122.0
27.2
95.4
27.4
18.4
36.4
2.24
0.05
2
142.1
38.3
132.0
31.1
22.3
45.0
2.49
0.06
Per Week
Corn Grain
0
46.9
8.5
7.1
A
3.2
0.7
0.01
*
1
108.0
27.9
24.2
*
9.4
2.7
0.03
*
2
126.1
39.7
29.1
*
11.0
4.5
0.05
*
^Quantities not computed because constituent was not determined.
-------
t-o
oo
Table 55. Quantities of Nutrients (Pounds Per Acre) Removed by Crops Receiving Various Levels
of Sewage Effluent Per Week - 1967
Crop and Inches of Effluent Applied Per Week
Corn Grain Pa. 444 Corn Pa. 602-A*
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Sodium
Boron
19"
0
66.4
16.0
14.4
**
5.2
2.5
0.06
0.01
Row Spacing
1
73.8
20.4
16.6
**
6.5
2.6
0.06
0.01
2
80.5
25.1
19.3
**
7.2
1.0
0.02
0.01
38"
0
81.5
20.3
18.7
**
6.4
1.7
0.11
0.01
Row Spacing
1
60.9
18.5
13.9
**
5.7
1.9
0.02
0.01
2
68.0
19.9
15.0
**
6.0
0.7
0.01
0.01
0
90.7
20.8
20.0
**
6.9
2.6
0.08
0.01
Grain
1
87.8
24.0
22.8
**
7.1
2.9
0.09
0.01
2
82.6
26.2
21.8
**
7.1
1.0
0.05
0.01
0
84.8
16.3
106.9
25.9
17.1
28.8
0.19
0.03
Silage
1
94.7
22.5
110.3
20.9
15.5
35.6
1.40
0.06
2
112.1
30.1
127.4
20.2
17.6
36.8
1.75
0.07
*Nineteen inch row spacing.
**Less than 0.10% Ca in tissue, generally less than 6.8 pounds per acre.-
-------
Table 56. Quantities of Nutrients (Pounds Per Acre) Removed by Crops Receiving Various Levels
of Sewage Effluent Per Week - 1969
VO
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Sodium
Boron
Corn
0
265.
28.
128.
34.
18.
38.
0.
0.
4
1
0
2
7
4
38
06
Crop
Silage
1
224.
32.
120.
31.
22.
48.
1.
0.
and
Pa.
9
7
0
2
3
0
51
06
Inches of
890-S
2
235.6
43.1
146.5
28.3
25.0
51.4
1.70
0.07
Effluent Applied
Corn
0
173
23
116
36
14
34
0
0
.1
.5
.4
.7
.7
.5
.10
.08
Per Week
Silage Pa.
1
258.
30.
145.
27.
22.
47.
1.
0.
8
1
4
7
2
8
97
08
602 -A
2
198.
58.
97.
16.
18.
33.
1.
0.
1
7
0
3
3
7
83
05
-------
Table 57. Quantities of Nutrients (Pounds Per Acre) Removed by Reed Canary-grass Receiving Two
Inches of Sewage Effluent Per Week. 1965-1969
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Sodium
Boron
1965
353.1
40.0
321.9
62.0
29.8
187.6
4.76
0.10
1966
272.2
33.4
250.5
28.8
18.9
122.0
1.18
0.05
1967
328.9
55.9
342.7
64.6
40.6
202.6
4.69
0.10
1968
356.2
47.2
254.8
40.7
27.9
169.6
3.09
0.05
1969
354.5
47.2
214.4
48.7
36.2
173.5
2.68
0.11
-------
Table 58. Average Concentration (mg/1) of Various Constituents in Wastewater Applied to the
Rotation Crops at Rates of One and TVro Inches Per Week - 1963-1969
1963
Constituent
Phosphorus
MBAS
Nitrate -N
Organic-N*
Potassium
Calcium
Magnesium
Sodium
Manganese
Chloride
Boron
pH
1
9.680
3.17
5.7
7.3
17.1
32.4
18.5
46.0
**
43.4
**
7.3
2
9.720
3.20
5.8
7.3
16.8
32.3
19.0
46.9
**
43.9
**
7.3
Concentration (mg/1)
1964 1965 1966
1
8.620
1.47
14.9
3.7
16.4
35.6
19.2
32.2
**
40.0
0.40
7.2
2
8.545
1.54
13.8
2.8
15.3
35.0
19.1
34.2
**
38.9
0.40
7.3
1
6.310
1.09
6.3
2.9
19.9
24.8
13.4
36.0
**
42.7
0.32
7.5
2
6.935
0.98
5.9
2.5
20.6
25.3
14.0
35.7
**
43.8
0.32
7.6
1
5.970
0.33
8.1
6.5
20.6
30.1
19.8
41.4
0.08
54.4
0.36
7.6
2
5.370
0.36
8.0
4.6
19.2
28.9
18.4
38.6
0.08
51.4
0.36
7.7
1967
1
4.930
0.26
5.4
4.0
18.4
22.6
11.3
39.5
0.16
48.9
0.42
7.6
6
0
5
4
18
22
12
40
0
45
0
7
2
.725
.30
V
.2
.0
.6
.6
.2
.0
.12
.0
.41
.8
*Values included aiimoniacal nitrogen. For the period 1965-1967, values are underestimated due to
loss of undetermined amounts of ammoniacal nitrogen during analysis. Method of analysis changed
in 1968.
**Values not determined.
-------
Table 58. (continued)
ts)
Constituent
Phosphorus
MBAS
Nitrate-N
Organic-N
!Ananoniacal-N
Potassium
Calcium
Magnesium
Sodium
Manganese
Chloride
Boron
pH
•*>>IMHH>IIIWIII»HIV^BI*^^**IM0VVvall»^alh*IIM»ll»^^^«VI'^WVMK-«ft^>^Ha
1968
1
5.345
0.50
4.7
2.9
15.7
16.7
20.9
10.6
37.4
0.36
50.6
0.38
7.6
*VHM^^M*ftaW^WffMmtHmplWVHHIBVHH^^MWWtf4IIH«l»^VI**^
Concentration
2
7.105
0.56
4.2
3.8
14.6
17.1
20.2
10.4
40.8
0.18
41.2
0.40
7.7
ri^*IW^W.^*B4IHM«**aH^^^M^^
(mg/1)
1
4.675
0.57
5.8
7.8
11.4
15.2
34.6
17.4
51.5
0.12
60.6
0.34
7.8
,^v^WMBMV4HHV^IHIflflHHHflflwlflflMflflw^H^VVIHIIIfll^^MaflflMflflHflMHflflwwH»HVVVVH*vvMv^»*vv
1969
2
6.560
0.54
5.1
4.8
12.8
13.8
32.0
16.3
52.8
0.10
44.4
0.38
7.9
-------
Table 59. Average Concentration (mg/1) of Various Constituents Applied to the Reed Canary-grass
Area - 1965-1969
Constituent
Phosphorus
Nitrate-N
Organic-N*
Ammoniacal-N
Potassium
Calcium
Magnesium
Sodium
Manganese
Chloride
Boron
PH
1965
6.935
6.1
2.5
-
20.6
25.3
14.0
35.7
-
43.8
0.36
7.6
1966
7.690
7.9
7.1
-
20.4
26.6
15.7
39.2
0.06
57.4
0.36
7.9
Year
1967
7.695
5.2
5.1
-
15.5
22.7
12.4
35.5
0.05
52.2
0.33
7.8
1968
8.450
4.0
3.9
15.7
16.6
25.8
13.1
41.0
0.15
48.0
0.40
7.7
1969
4.185
2.8
2.8
13.0
9.8
24.4
11.3
30.0
0.07
39.4
0.23
7.8
*Values for 1965-1967 include ammoniacal nitrogen. These are understated due to loss of
undetermined amounts of ammoniacal nitrogen during analytical procedure. Method of analysis
changed in 1968.
-------
Table 60. Total Amounts (Pounds Per Acre) of Various Constituents in Sewage Effluent Applied to
the Rotation Crops at Rates of One and Two Inches Per Week - 1963-1969
1963
Constituent
Phosphorus
MBAS
Nitrate-N
Organic-N*
Potassium
Calcium
Magnesium
Sodium
Manganese
Chloride
Boron
Inches of
Effluent
1
52.
17.
31.
39.
93.
176.
100.
250.
64
24
0
7
0
2
6
1
**
236.
**
24
0
2
105.71
34.80
63.1
79.4
182.7
351.3
206.6
510.0
**
477.4
**
48
Amounts Applied (Ib/a)
1964 1965 1966
1
64.45
10.99
111.4
27.7
122.6
266.3
143.6
240.8
**
299.1
3.0
33
2
127.78
23.03
206.4
41.9
228.8
523.4
286.5
511.4
**
581.7
6.0
66
1
41.46
7.16
41.4
17.1
130.8
163.0
88.0
236.6
**
280.6
2.1
29
2
91.14
12.88
77.5
32.8
270.7
332.5
184.0
469.2
**
575.6
4.2
58
1
43.28
2.39
58.7
47.1
149.4
218.2
143.6
300.2
0.6
394.4
2.6
32
2
77.87
5.22
116.0
66.7
278.4
419.1
266.8
559.7
1.2
745.4
5.2
64
1967
1
27.92
1.45
30.5
23.6
104.2
128.0
64.0
223.8
0.9
276.9
2.4
26
2
76.15
3.40
59.5
47.1
210.7
256.0
138.2
453.2
1.4
509.8
4.6
52
*Values included ammoniacal nitrogen. For the period 1965-1967 values are underestimated due to
loss of undetermined amounts of ammoniacal nitrogen during sample analysis. Method of analysis
changed in 1968.
**Values not deteimined.
-------
Table 60. (continued)
en
1968
Constituent
Phosphorus
MBAS
Nitrate-N
Organic -N
Aranoniacal-N
Potassium
Calcium
Magnesium
Sodium
Manganese
Chloride
Boron
Inches of
Effluent
1
24.22
2.28
21.1
13.1
58.0
75.7
94.7
48.0
169.5
1.6
229.4
1.7
20
2
54.40
5.20
37.7
34.4
132.3
155.0
183.1
94.2
370.0
1.6
373.0
3.6
40
1969
1
16.94
2.08
21.0
28.3
41.3
55.1
, 125.4
63.1
186.7
0.4
219.8
1.2
16
2
47.55
3.94
37.3
34.8
92.8
100.1
232.0
118.2
382.8
0.7
321.3
2.8
32
-------
Table 61. Total Amounts (Pounds Per Acre) of Various Constituents Applied to Reed Canarygrass
Receiving Two Inches of Sewage Effluent Weekly - 1965-1969
Constituent
Phosphorus
Nit rate -N
Organic-N*
Ammoniacal-N
Potassium
Calcium
Magnesium
Sodium
Manganese
Chloride
Boron
Inches of
Effluent
M^— WH^^B^WMA^^^^MHM^W^^^^^^— MM
1965
125.7
110.6
45.3
-
373.4
458.6
253.8
647.1
-
794.3
6.5
80
—Hill.— .Ill .. Jin™ —III-—.- Ill .11 — ..—-III Ul
1966
135.9
139.6
125.5
-
360.5
470.1
277.5
692.8
1.1
1014.9
6.4
78
<^*««»^^B«H^HH.^»^H.^^^H^^HV^H^VP^H^HIB^^^V^^
Year
1967
163.9
110.7
108.6
-
330.1
483.5
264.1
756.1
1.1
1112.8
7.7
94
•^•••^•H»lp^^*alVh^VBII^>^MIBV.MM^^BMta^W— BH^^
1968
187.6
88.8
86.6
348.6
368.6
572.9
290.0
910.4
3.3
1065.8
8.9
98
^B^^^OM— ^M.W^^I»^^M^^M-^^^
1969
94.8
63.4
63.4
294.6
222.0
552.8
256.0
682.0
1.6
892.3
5.2
100
*Values for 1965-1967 include ammoniacal nitrogen. These are understated due to the loss of
undetermined amount of ammoniacal nitrogen during analytical procedure. Method of analysis
changed in 1968.
-------
Table 62. Renovation Efficiency (Percent) of Crops at One and Two Inch Per Week Applications -
1963
Crop and Inches of Effluent -Applied Per Week
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Red Clover
1 2
*
49.1 22.9
281.0 130.0
73.0 34.7
21.8 10.7
Alfalfa
1 2
* *
43.6 30.2
176.7 124.6
29.1 13.3
11.1 7.2
Corn Grain
1
174.5
51.9
24.5
0.2
7.6
2
89.5
31.0
18.1
0.1
4.6
Wheat Grain
1
91.9
30.5
12.4
0.8
4.0
2
59.6
19.3
6.3
0.5
2.6
Wheat Straw
1
13.8
2.5
11.6
2.0
1.1
2'
11.5
2.3
10.1
1.4
0.7
*Not computed for legumes because of unknown contribution from symbiotic nitrogen fixation.
-------
Table 63. Renovation Efficiency (Percent) of Crops at One and Two Inches Per Week Applications
1964
CO
Crop and Inches of Effluent Applied Per Week
Red Clover Corn Grain Corn Stover Oat Grain
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Boron
1
*
52.0
260.6
44.2
28.2
33.9
9.0
2
*
24.1
121.6
15.4
10.8
19.0
5.0
1
76.4
20.9
24.7
1.9
4.9
1.2
1.3
2
52.0
10.2
12.0
0.9
2.3
0.5
1.0
1
59.7
13.3
165.1
23.8
22.8
10.4
1.7
2
43.6
20.1
99.3
12.4
11.5
4.8
1.7
1
31.1
27.7
22.3
2.1
4.9
1.4
1.0
2
20.6
11.1
8.3
0.9
2.0
0.3
0.7
*Not computed for legume of unknown contribution from symbiotic nitrogen fixation.
-------
Table 64. Renovation Efficiency (Percent) of Crops at One and Two Inches Per Week Applications
1965
Alfalfa
Nutrient*
Nitrogen*
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Boron
1
**
63.6
188.5
32.1
17.9
37.9
7.6
2
**
38.7
118.7
19.2
10.7
22.8
4.8
Crop and Inches of Effluent Applied Per Week
Corn Grain Corn Silage Oat Grain
1
165. 6
78.0
26.1
0.6
11.2
0.9
1.0
2
88.1
40.5
13.3
0.9
6.1
0.3
0.5
1
183.6
38.9
61.9
17.1
17.3
10.3
1.9
2
99.8
21.8
40.2
8.3
8.2
5.8
1.0
1
87.7
26.3
11.4
1.4
3.6
0.8
0.5
2
32.4
11.5
5.1
0.6
1.6
0.4
0.2
Oat Straw
1
28.9
15.2
88.9
12.7
6.1
21.7
1.4
2
5.8
8.4
39.5
5.9
2.8
13.5
0.5
*Values are overestimated due to the loss of undetermined amounts of ammoniacal nitrogen in
effluent sample analysis.
**Not computed for legume because of unknown contribution from symbiotic nitrogen fixation.
-------
Table 65. Renovation Efficiency (Percent) of Crops at One and Two Inches Per Week Applications
1966
Crop
Corn Silage
Nutrient
Nitrogen*
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Sodium
Boron
1
115.3
64.9
65.9
13.0
13.2
9.5
0.8
2.0
2
77.8
50.8
48.9
7.7
8.6
6.2
0.4
1.0
and Inches of
Effluent Applied Per Week
Corn Grain
1
102.1
64.4
16.2
***
6.5
0.7
0.1
***
2
69.0
51.0
10.4
***
4.1
0.6
0.1
***
Alfalfa
1
**
59.6
151.7
24.5
10.8
21.7
0.6
4.0
2
9s*
37.9
89.8
11.5
6.3
9.5
0.3
2.0
*Values are overestimated due to undetermined loss of ammoniacal-N in effluent sample analysis.
**Not determined because of unknown contribution from symbiotic nitrogen fixation.
***Not computed because constituent was not determined.
-------
Table 66. Renovation Efficiency (Percent) of Crops at One and Two Inches Per Week Application -
1967
Crop and
Corn Pa. 60 2 -A*
Silage
Nutrient
Nitrogen**
Phosphorus
Potassium
Calciun
Magnesium
Chloride
Sodium
Boron
1
175.0
80.6
105.8
16.3
24.2
12.8
0.62
2.5
2
105.2
39.5
60.6
7.9
12.7
7.2
0.38
1.5
Inches of Effluent Applied Per Week
Corn Grain Pa. 444
Grain
1
162.2
86.0
21.9
****
11.1
1.0
0.04
0.4
2
77.5
34.4
10.3
****
5.1
0.2
0.02
0.2
19" Row
1
136.4
73.1
15.9
****
10.2
0.9
0.03
0.4
Spacing
2
75.5
33.0
9.2
****
5.1
0.2
0.04
0.2
38" Row
1
112.6
66.3
13.3
****
10.0
0.7
0.04
0.4
Spacing
2
63.8
26.1
7.1
****
4.2
0.1
0.02
0.2
Alfalfa
1
***
76.3
173.8
24.8
17.2
28.0
0.52
2.9
2
***
31.9
99.2
12.5
9.0
18.6
0.28
1.7
*Nineteen inch row spacing.
**Values are overstated due to the loss of undetermined amounts of ammoniacal nitrogen in
effluent sample analysis,
***Not computed for legume because of unknown contribution from symbiotic nitrogen fixation.
****Not computed because tissue content was less than 0.10% Ca, but generally was less than 5.3%
renovation efficiency.
-------
tsj
Table 67. Renovation Efficiency (Percent) of Crops at One and Two Inches Per Week Application
IQfiQ
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Sodium
Boron
Crop and Inches
Corn Silage Pa. 890-S
1 2
248.2 142.3
204.8 90.6
218.1 146.4
24.9 12.2
35.4 21.2
21.8 16.0
0.81 0.44
4.9 2.5
of Effluent Applied Per Week
Corn Silage
1
285.6
177.7
263.9
33.1
35.2
21.8
1.04
6.5
Pa. 602 -A
2
120.1
123.4
96.9
7.0
15.5
10.5
0.48
1.8
-------
Is)
Table 68. Renovation Efficiency (Percent) of Reed Canary-grass at Two Inches of Sewage Effluent
.Application - 1965-1969
Nutrient
Nitrogen*
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Sodium
Boron
1965
226.4
31.8
86.2
13.5
11.7
23.6
0.7
1.0
1966
102.7
24.6
70.0
6.1
6.9
12.2
0.2
0.9
Year
1967
150.0
34.2
103.1
13.4
15.4
18.0
0.6
1.3
1968
68.2
25.2
68.6
7.1
9.6
15.9
0.3
0.6
1969
75.8
49.0
96.6
8.8
13.9
19.5
0.6
1.9
*Values are overstated in 1965-1967 due to loss of ammoniacal nitrogen during effluent sample
analysis. Method of analysis corrected in 1968.
-------
200
160
120
UJ
1
o
£ 80
40
y=- 0.63X41822
R2 » 0.71
40 80
Nitrogen - Ib per acre
120 160 200 240 260
Figure 42. Regression of Removal "Efficiency on Nitrogen Loading.
-------
tn
100 _
y • -0.66 X + 93.4
R2 = 0.72
0 20 40
Phosphorus- Ib. per acre
80
100
120
Figure 43. Regression of Removal Efficiency on Phosphorus Loading.
-------
is split into 20 to 50 doses at weekly intervals hence the larger
total amount never reaches a toxic level. However,if the small incre-
mental amounts accumulated,excessive quantities of boron might become
toxic to vegetation. A later section will describe the investigation
of the boron relationships in greater detail.
The removal of nutrients in the harvested crops was computed as a
renovation efficiency in Tables 62 through 68. Discussion will be
focused on the two key eutrophic nutrients, N and P. The removal
efficiencies of the individual crops in comparable years are summar-
ized in Table 69. On the rotation crop area the highest removal
efficiency for nitrogen was obtained with silage corn and for phos-
phorus with grain com. Grain corn was substantially better than oats
in removing both nitrogen and phosphorus. Generally as the nutrient
load increased the removal efficiency decreased. This is obvious
within years by comparing the 1-inch and 2-inch treatment values and
is also shown when comparing the same crop in different years as indi-
cated in Figures 42 and 43. These linear regressions of amount of
nutrient load with removal efficiency were significant at the 0.001
level. The R^ value for the regression equations were 0.71 for nitro-
gen and 0.72 for phosphorus.
Table 69. Average Removal Efficiencies of Various Crops for Nitrogen
and Phosphorus in Comparable Years
Removal Efficiency - %
1965-1967 1964-1965
N P N
Crop 1" 2" -1" 2" 1" 2" 1"
Alfalfa
Corn -Grain
Corn-Silage
Oats -Grain
*
143.3
158.0
*
78.2
94.3
66.5
76.1
61.5
36.2
42.0
37.4
121.0
59.4
70.0
26.5
49.5
27.0
25.3
11.3
*Not computed because of unknown inputs of nitrogen from symbiotic
nitrogen fixation.
The inherent capacities of the individual crops can also be compared
by examining the absolute amounts of N and P removed. These data are
expressed in Table 70 as amounts removed per acre per crop year and
indicate the obvious superiority of reed canarygrass in removing both
N and P. Oats were least effective and corn silage was better than
corn grain, particularly with respect to N, and also with respect to
P at the higher nutrient loading level. The legume hays were just
146
-------
Table 70. Mounts Removed in Harvested Crops Per Acre Per Crop Year
on Wastewater Treated Areas - 1963-1969
No. of
Harvest Years
Nitrogen
1"
2"
Phosphorus
1" 2"
Alfalfa Hay
Red Clover Hay-
Corn
Corn Silage
Oats
Reed Canarygrass
3
2
5
4
2
5
247.7
252.7
100.9
145.7
46.8
220.7
227.0
111.2
140.6
45.9
333.0
25.2
30.3
24.8
24.2
14.9
31.4
27.0
28.7
36.5
12.5
44.6
about as effective as corn in removing phosphorus on the wastewater
treated areas. Nitrogen removals in the legumes were higher than in
corn grain or silage but it is not known what fraction may have been
provided by symbiotic nitrogen fixation. It is known that high levels
of nitrogen fertilization suppress nodulation and presumably symbiotic
fixation by the nodule bacteria. Hence the legumes may be using a
substantial part of the nitrogen added in the wastewater. Water
quality data in the wastewater treated plots indirectly indicate that
the legume hays were utilizing the added nitrogen, inasmuch as the
nitrate content in the soil water was lower at sampling sites located
in the legume hay strips than in the corn strips.
Removals of potassium and chloride were greatest with the legume hays,
slightly less with corn silage and substantially less with both grains,
corn and oats. Removals of potassium by the legumes is so great that
future fertility management might require additions of fertilizer
potash to maintain good yields. Removals of potassium and chloride
were highly correlated but potassium was removed in greater quantities
. in all crops. The quantities of both cations and anions removed by
the legumes and silage corn result in a substantial desalination of
the wastewater, equivalent to approximately 20-25% of the cations and
anions present in the wastewater.
Boron although added in the smallest total amounts was also removed in
small amounts. The removal efficiency of the non-legume crop for
boron was poor, and even the legumes did not reach 10%. The lowest
average removal efficiencies occurred with sodium. Sodium was not
only strongly excluded from the whole plant, it was even more severely
excluded from the grain. This means that most of the sodium will
either be retained by the soil through cation exchange reactions or
move into the groundwater.
Nutrient additions to the reed canarygrass were 50% to 200% greater
than on the crop rotation area because of the larger amounts of efflu-
ent applied. As a consequence removal efficiencies are not as great
147
-------
but total amounts of nutrients removed were all substantially higher.
In 1969 the 354 pounds of nitrogen removed was equivalent to a removal
efficiency of 75.8% whereas the 236 pounds of nitrogen removed by
silage corn that year was equivalent to a removal efficiency of
142.3%. In that year the reed canarygrass area received 421 pounds
of nitrogen in 100 inches of wastewater throughout the year while the
silage corn was receiving only 165 pounds of nitrogen from mid-May to
mid-September (16 weeks). The comparative capacities of reed canary-
grass and corn silage for removing nitrogen and phosphorus are shown
in Figures 44 and 45.
In conclusion it can be stated that all harvested crops make a
significant contribution to renovating the wastewater. The fate of
the nutrients not absorbed and removed in the harvested crops will be
described in subsequent sections.
148
-------
vo
4OO
300
e
O
« 200
-0
—
I
c
•
i 100
0
<0
o
lO
R.C.
o
g
C.
1965
CM
m
CM
CM
N-
CM
lO
CO
•—
CM
—
0>
R.C. C. R.C.
f-
g
—
CM
C.
1966 1967
CM CM
(0
10
0
o
1 L
m
m
10
s
l:Jlll,
(O
lO
M
R.C. C. R.C. C.
1968 1969
year
Figure 44, Nitrogen Added in Applied Sewage Effluent and Removed in Harvested Reed Canary-grass
and Silage Corn.
-------
en
O
54
«
O
«36
Q.
.d
i
M
3
O.
O
fi ,Q
OL 18
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-------
Soil Percolate Water Quality
Previous Studies. It has been indicated that substantial amounts of
various constituents in the applied wastewater were removed in
harvested crops and hence changes in the chemical quality of the per-
colating wastewater can be expected from operation of this segment of
the living filter system alone. In addition it can be expected that
other biological and physico-chemical reactions could influence the
final equilibrium concentrations of the various chemical elements in
the percolating water which is derived from either the applied waste-
water or from natural precipitation.
A review of the literature indicates that many of the earlier studies
of water quality changes in passing through soil were with systems
involving raw sewage or primary effluents in infiltration basins or
spreading basins with relatively high loading rates. Baars (31)
reported that in Europe effluent from surface infiltration basins
commonly formed the source of recharge for the ground water supply.
In a study in the Netherlands he noted that the percolate from the
basins was significantly lower in nitrate because of denitrification.
Although suspended matter was reduced by 100 percent, chloride, bi-
carbonate and hardness showed little change.
In the United States, one of the earliest instances of the application
of sewage effluent to the soil was described by Laverty (32). He
states that the spreading of wastewater by means of ditches and canals
began in 1916 in the San Gabriel Valley, California in order to supple-
ment the ground water. More detailed studies were not made until 1930
when Goudey (33) investigated the spreading, on sand beds, of sewage
plant effluent. It was found that the quality of the ground water was
not significantly affected after the percolate had travelled 25 feet.
More recently, Stone and Garber (34, 35) reported that in sewage
effluent percolated through seven feet of soil, nitrate, phosphate,
potassium and boron were measurably removed. On the other hand, there
were insignificant changes in concentration of such constituents as
calcium, magnesium, sodium and chloride. Similar results were obtained
in a different study (36) after the effluent percolated through 13
feet of soil. Throughout this depth nitrates however steadily in-
creased, phosphorus disappeared within the upper foot and potassium
decreased by 50 percent below seven feet.
In a study involving five California soils (37) it was found that after
an initial decrease attributed to dilution, the concentrations of
magnesium, sodium, ammonia-nitrogen, and phosphate increased and, at a
depth of three feet, approached the levels of the applied sewage. At
the same depth calcium in the percolate increased two to five times;
chloride remained essentially constant while nitrate decreased to trace
amounts from an original concentration that averaged 0.8 ppm.
151
-------
After irrigating reed canarygrass with effluent from a meatpacking
plant, Henry et al. (24) noted that calcium, potassium and magnesium
increased in tKe percolate at a depth of four feet. They attributed
this to replacement of these ions on the exchange complex by sodium
which was present in the effluent at a much higher concentration (680
ppm). There was little change in the concentrations of sodium and
chloride although phosphorus was sharply reduced.
Greenberg and Gotaas (38) reported only few chemical changes in final
sewage effluent after it had percolated 13 feet. Calcium, magnesium,
sodium and potassium did not change significantly. Ammonia-nitrogen
and phosphate were entirely removed within the upper foot but nitrate
and organic nitrogen increased. They concluded that nitrification was
responsible for the increase in nitrate concentration (24 ppm to 68
ppm) and conceded that were it not for dilution by the ground water,
the percolate would have been unfit for drinking according to the
standards set by the United States Public Health Service (39).
Investigations by Greenberg and McGauhey (40) and by Greenberg and
Thomas (41) produced similar results except that potassium, in this
case, decreased by 50 percent, chloride remained unchanged, but
nitrate-nitrogen increased by several hundred percent evidently at the
expense of ammonia-nitrogen and nitrite-nitrogen.
As the impact of pollution and the involvement of ABS became more
evident and as methods for its deteimination were developed, ABS also
became a constituent of interest to those studying the chemical changes
of percolating effluent.
The removal of ABS from percolating wastewater was effected by adsorp-
tion by the soil and by degradation by soil microorganisms. In column
studies, Klein et al. (42) found that ABS was adsorbed mostly in the
upper 2.5 cm ofsbTT. Biological degradation was also highest in this
zone possibly on account of the favorable oxygen status that existed.
They also found that ABS was rapidly desorbed from the soil to an
extent of 80 percent when leached with ABS-free water. An evaluation
of the relative importance of adsorption and degradation of ABS in the
renovation process has not met with agreement. The authors found that
biological degradation played a minor role in the removal of ABS from
the percolating effluent. On the other hand, Robeck et al. (43) found
that the reduction of ABS was due almost entirely (97 percent), to
degradation. The mode of degradation of ABS has been studied by
McKinney and Symons (44). They postulated that the incomplete degrada-
tion of ABS was due to the presence of a quaternary carbon atom within
the molecule. Where this was absent, as in LAS, biological degradation
would approach completion. Evidence in support of this was later cited
by Sawyer and Ryckman (45).
The removal of ABS from percolating wastewater has been undoubtedly,
adequate. Highly treated, activated-sludge sewage effluent was used
152
-------
in a reclamation study by McKee and McMichael (46). At a depth of
eight feet they found that the percolate showed an increase in
calcium and nitrate concentrations. Magnesium and chloride remained
essentially constant but surfactant (ABS) along with sodium, potassium,
ammonium and phosphate decreased significantly.
A high degree of renovation of sewage plant effluent was reported by
Pennypacker et al. (47) in the irrigation of forest land. At applica-
tion rates oF~bne inch per week and two inches per week. The removal
of ABS by the forest floor (two-inch depth) amounted to 86 percent and
65 percent respectively. However, at a depth of one foot the removal
was 95 percent and 98 percent respectively. In the forest floor,
nitrate-nitrogen increased three-fold but at a depth of one foot it was
reduced by 68-82 percent. Other removals at this depth included
organic-nitrogen by 75-86 percent and phosphorus by 99 percent.
Chloride was slightly lower in the percolate. The authors further
noted that various constituents in the effluent tended towards equi-
librium at certain depths. For example, phosphorus and potassium
equilibrated within the upper foot while the concentrations of ABS,
nitrate-nitrogen, calcium, magnesium, sodium and chloride leveled off
at four feet. Laverty et.al/ (48) also reported that intermittent
spreading of primary sewage effluent improved its quality prior to
injection into recharge wells. Nitrate, phosphorus and ABS decreased
but chloride was not removed.
These studies on percolating effluent have indicated certain trends
with regard to chemical changes in the effluent. Apart from potassium,
the cations generally showed little change. In the case of anions,
ABS and phosphate were sharply reduced while chloride which shows al-
most no tendency towards ion adsorption by soil, remained unchanged.
Nitrate, however, depending on the conditions prevailing in a particu-
lar system may either increase or decrease with the depth of percola-
tion.
Procedures. Samples of water percolating through the soil profile
were secured using suction lysimetersl in order that samples might be
collected whether the percolating water was moving downward under
tension gradients or in saturated flow.
Each lysimeter, as illustrated in Figure 46 consists of a porous
ceramic cup (1 7/8 in. O.D. x 2 7/8 in. long) cemented to a plastic
tube (1 7/8 in. O.D.) at the lower end. The upper end of the plastic
tube is sealed with a rubber stopper (No. 8) through which passes a
short length of copper tubing (3/8 in O.D.). A short length of thick-
walled rubber tubing bearing a Hoffman screw clamp is fitted over the
Obtainable from Soilmoisture Equipment Company, 3005 De La Vina
St., Santa Barbara, California.
153
-------
en
(a)
n
2 7/8, in |
Thick-walled rubber tubing
Copper tubing
(3/8 in. O.D.)
Rubber stopper
(No. 8)
Plastic tube
(1 7/8 in. O.D.)
Cemented joint
Porous ceramic cup
(1 7/8 in. O.D.)
To suction flask and
portable, hand-operated,
piston pump
Thin rigid tubing
Top soil mounded
Soil surface
Silica flour
Figure 46, Diagram of (a) Suction Lysimeter with Single Hole Stopper Assembly and (b) Lysimeter
Installed at Depth of 48 Inches with Tubing Inserted to Remove Sample
-------
end of the copper tubing protruding above the stopper.
Prior to installation each lysimeter was washed several times with
dilute HC1 (approximately 0.01N) and then rinsed free of chloride with
distilled water. This preliminary washing was carried out because it
was previously noticed that a rather alkaline reaction (pH 9) was
imparted to distilled water flowing into the porous ceramic cup,
probably on account of dissolution of bases in the walls of the cup
itself. Washing was effected by placing the lower end of the lysi-
meter in the dilute acid and partially evacuating the chamber, thus
allowing the liquid to flow through the walls of the cup.
The lysimeters were installed at three depths, namely, 6 inches, 24
inches and 48 inches. Installation in the com rotation areas was
completed prior to start of irrigation in 1965. Installation in the
reed canarygrass area was completed in the summer of 1965. Instal-
lation, as illustrated in Figure 46, was carried out with the help of
a screw-type auger that made a hole 1 3/4 inches in diameter. The
sides of each hole were smoothed by forcing a two inch aluminum pipe
down to the required depth, with allowance being made for a 1/2 inch
layer of silica flour2 on the bottom of the hole. After the lysimeter
was inserted in the hole more silica flour was packed around its
entire length. Finally, top soil was packed around the lysimeter at
the soil surface.
In operating the suction lysimeter, a portable, hand-operated piston
pump was attached to the plastic tube via the thick-walled rubber
tubing, the chamber partially evacuated to 25 inches of mercury and
the screw clamp tightened. The hydraulic gradient across the porous
cup induces flow of water into the chamber until tension forces are
balanced.
To remove the samples, the clamp was loosened, releasing the vacuum,
and suction was applied through a suction flask to a length of copper
or rigid plastic tubing inserted to the bottom of the lysimeter. The
total volume of the sample was measured and the entire sample, if less
than one liter, or a one-liter subsample was poured into polyethylene
bottles. Samples were collected on a weekly basis throughout each
year regardless of whether or not wastewater was applied. During the
period of application, the collection was made, generally within 24
hours of the end of each weekly application.
Obtainable from Pennsylvania Glass Sand Corporation, Maple ton,
Pennsylvania
155
-------
Suction Lysimeter Data
The mean annual concentration of various constituents in suction
lysimeter samples at three depths in the crop rotation area (Agronomy
Area A-0, A-l and A-2) are given in Tables 71 through 83 on pages 166
to 178, Similar data for the reed canarygrass area (Agronomy Area A-3)
occur in Table 84 on page 179.
The significance of the main effects in the com rotation area for
treatments (0, 1 and 2 inches per week) within depths (6", 24" and
48") and within years (1965-1969) is summarized in Tables 71 to 83 on
pages 166 to 178 and the years effect within treatments and within
depths in Tables 85 to 97 on pages 180 to 192.
The data in Table 71 indicate that phosphorus concentration decreases
drastically between the upper six inches and the 24-inch depths on
all areas. At the 6-inch depth, concentrations in the 2-inch treat-
ment area were significantly greater than in both the control area
(0-inch) and the one-inch treatment area (Figure 47). At the 24-inch
depth differences in phosphorus concentration between wastewater
treatments was non-significant in three of the five years (Table 71
and Figure 48). At the 48-inch depth the differences were unrelated
to wastewater treatment or non-significant (Table 71 and Figure 49).
The year effects (Table 85) were erratic. There was a general tendency
on the wastewater treated areas for phosphorus concentration to in-
crease through 1967, levelling off or decreasing in 1968 and 1969.
The nitrate nitrogen with its greater chemical mobility shows no con-
sistent depth pattern and an erratic wastewater treatment pattern,
particularly at the six inch depth (Table 72). The years effect within
wastewater treatments and within depths (Table 86) was highly signifi-
cant for all depths and appears to be a reflection of the extent to
which corn, either grain or silage, rather than alfalfa-grass hay
occupied the treatment area. In the period 1965-67 corn occupied 281 .
of the area, in 1968 and 1969 it was 1001 but with a heavy weed in-
festation in 1968 and weed-free in 1969. The nitrate-nitrogen values
at the 48-inch depth (Figure 50) might be regarded as the break-through
nitrate values which have escaped the biological removal zone and hence
might be expected to reach the groundwater. These values in the 1965-
67 period ranged from 3.4 to 5.3 mg NOsN per liter in the control area,
from 3.8 to 8.2 in the 1-inch wastewater area and from 7.0 to 9.7 in
the 2-inch wastewater area. In 1968 when heavily weed-infested corn
occupied 100% of the area the nitrate nitrogen values at the 48-inch
depth were 4.3, 5.8 and 9.6 mg NQ$-N per liter, respectively in the
control, 1-inch and 2-inch treatment areas. In 1969 when weed-free
corn occupied 100% of the area the nitrate values were 9.3, 7.7 and
14.0 mg NOs-N per liter, respectively, for the same treatment areas.
The value of 14.0 mg, in 1969, exceeds the recommended limit of the
Public Health Service, 10 mg N03-N per liter.
156
-------
0.70
0.60
0.50
0.40
I 0.30
«
a.
E
a. 0.20
0.10
0.00
P in suction lysimeters at 6 inch depth
i
/
/
Wastewater levels
. 0 inch per week
I inch per week
2 inches per week
/
$
/
N
\
'65
'66 '67
Year
'68
'69
Figure 47, Msan Annual Phosphorus Concentration in Suction Lysimeters
at the Six Inch Depth in the Corn Rotation Area Receiving
0, 1, and 2 Inches of Wastewater at Weekly Intervals,
Apr. - Nov., 1965-1969.
157
-------
0.10
0.08
0.06
•* 0.04
o>
E
CL 0.02
0.00
P in suction ly si meters at 24 inch depth
Wastewate-r level
0 inch per week
I inch per week
2 inches per week
'65
'66
'67
Year
'68
'69
Figure 48. Msan Annual Phosphorus Concentration in Suction Lysimeters
at the 24-Inch Depth in the Corn Rotation Area Receiving
0, 1, and 2 Inches of Wastewater at Weekly Intervals,
Apr. - Nov., 1965-1969.
158
-------
0.10
0.08
0.06
o>
- 0.04
k.
O)
a.
0.02
0.00
P in suction lysimeters at 48 inch depth
Wostewater level
x
0 inch per week
i inch per week
2 inch per week
'65
'66 '67
Year
'68
'69
Figure 49. Mean Annual Phosphorus Concentration in Suction Lysimeters
at the 48-Inch Depth in the Corn Rotation Area Receiving
0, 1, and 2 Inches of Wastewater at Weekly Intervals,
Apr. - Nov., 1965-1969.
159
-------
It is probable, therefore, that corn grown without a cover crop on a
well drained soil would not be satisfactory for controlling the leak-
age of nitrate into the groundwater when two inches of treated waste-
water is applied weekly. On the other hand corn grown in a no-till
sod culture system may do an adequate job.
The data in Table 84 indicate that a perennial grass, reed canarygrass,
which received two inches of wastewater weekly, year round, and hence
more than twice as much total nitrogen as the corn rotation area, kept
the NOj-N concentration far below the P.H.S. limit. Figure 50 shows
the year by year variation of NO^-N at the 48-inch depth on the corn
rotation area and the reed canarygrass area. It is clear that a
harvested perennial grass would be advantageous in diminishing nitrate
leakage from wastewater treated areas.
Data for kjeldahl nitrogen and ammonium nitrogen (Tables 73, 74, 87,
88) were examined for statistical significance of treatments only in
1968 and 1969. Data for the earlier years was not available for
ammonium nitrogen and was unreliable for the kjeldahl nitrogen because
of an error in analytical procedure in 1965, 1966 and 1967. The years
effects were not examined because only 1968 and 1969 had reliable
values. Differences between the wastewater treatments for both kjeldahl
nitrogen and ammonium nitrogen were not significant in both 1968 and
1969. The ammonium nitrogen concentration in the lysimeter samples
was much lower than concentrations in the applied wastewater. The
latter ranged from 5.3 to 15.7 mg Iffy-N per liter whereas the range in
the lysimeter samples in the effluent treated plots was 0.41 to 1.08
mg per liter. Thus most of the Mfy-N was either adsorbed on exchange
sites, biologically transformed to protein by the microbes and higher
plants, or biologically transformed to nitrate.
Potassium which was present in the wastewater in mean annual concentra-
tions ranging from 13.5 to 20.6 mg/1 was substantially decreased in
concentration in percolating through the soil. Differences due to the
wastewater treatments (Table 75) were non-significant for all years at
the 6-inch depth. At the 24-inch and 48-inch depth the concentration
in the wastewater areas was significantly greater than in the control
only in 1968 and then only at the 51 level of significance. In 1969
the concentration at the 48-inch depth was significantly greater (51
level) in the control than in the 1-inch wastewater treatment but not
when compared to the 2-inch treatment. The year effects (Table 89)
were erratic at the six inch depth but in all three treatments the
potassium concentration at both the 24-inch and 48-inch depths tended
to decrease with time.
Calcium concentration in the wastewater also decreased substantially in
passage through the soil. Mean annual concentration in the wastewater
ranged from 20.2 to 35.6 mg/1 but at the 48-inch depth only from 5.4
to 11.8 mg/1 in the lysimeter samples from the wastewater areas.
Differences due to wastewater treatment (Table 75) were generally non-
160
-------
Ov
15
9>
I I0
CJ>
E
Z
I
ro
O -
z 5
0 control
i '
corn rotation
_. 2"
2n reed canarygrass
I
'65
'66
'67
year
'68
'69
Figure 50. Nitrate-N in Suction Lysimeters at the 48-Inch Depth in the Corn Rotation and Eeed
Canarygrass Areas.
-------
significant at the 6-inch depth except in 1967 when the 2-inch treat-
ment was significantly greater than the control and in 1967 when the
wastewater treatments were significantly less than the control. Con-
centrations of calcium at the 24 and 48-inch depths in the wastewater
treatments were generally higher than in the control in 1965 and 1966
but the differences became erratic in 1967, 1968 and 1969. As with
potassium the year effects (Table 90) were erratic at the 6-inch
depth but calcium concentration at the 24 and 48-inch depth tended to
decrease with time in the 1 and 2-inch wastewater treatments.
Like potassium and calcium, magnesium also decreased in concentration
substantially in passing through the soil. Mean annual magnesium
concentration in the wastewater ranged from 10.4 to 19.8 mg/1 and from
2.7 to 7.0 mg/1 in lysimeter samples from the 48-inch depth on the
wastewater treated areas. Wastewater treatments (Table 77) generally
had higher concentrations of magnesium than the control at all three
depths. Year effects on the control area were erratic and small, (Table
91). On the wastewater treated areas, magnesium concentration in the
lysimeter samples tended to decrease with time, particularly at the
24 and 48-inch depths.
The greatest increase in concentration of any constituent as a result
of wastewater application occurred with sodium and the differences were
highly significant (Table 78). Although the wastewater applications
increased the sodium concentration in the soil water 10 to 30 fold it
should be noted this concentration was substantially less than the
concentration of sodium in the applied wastewater. The latter ranged
in mean annual concentration from 32.2 to 52.8 mg per liter whereas
the lysimeter samples from the 48-inch depth in the wastewater areas
ranged from 19.1 to 32.3 mg per liter. Adsorption on the exchange
sites contributed to this decrease whereas uptake by plants was negli-
gible, the years effect (Table 92) was non-significant and -variable
in the control area and was erratic in the wastewater areas.
The difference in concentration of chloride between the control area
and the wastewater treated areas (Table 79) was not as great as with
sodium because chlorides were added to the control area with the
applied commercial fertilizers which contained potassium chloride.
However the differences were highly significant at all depths. The
chloride concentration in the lysimeter samples at the 48-inch depth
in the wastewater areas although large, ranging from 25.7 to 40.3 mg
per liter, were nevertheless smaller than in the applied wastewater,
38.9 to 60.6 mg per liter. Substantial quantities of chlorides were
removed in harvested crops and, as will be seen in the section on
soil chemical characteristics, significant amounts were adsorbed by
the soil. The years effect on chlorides (Table 93) was primarily a
decrease with time, showing up more consistently, beginning in 1967.
162
-------
Manganese concentrations in the lysimeter samples (Table 80) were very
low and substantially lower than in the applied wastewater, which had
a mean annual range from 0.08 to 0.36 mg Mn per liter. Significant
differences found at the 24 and 48-inch depths were expressed as
smaller concentrations in the 2-inch wastewater treatment. The years
effect was variable (Table 94). In the 2-inch treatment area only one
value exceeded the U.S. Public Health Service recommended criteria for
drinking water, 0.05 mg Mn per liter. At the 48-inch depth in the
control and one-inch treatment areas only the 1969 value did not exceed
the P.H.S. value. The mean value over the five-year period at the 48-
inch depth was 0.080, 0.060 and 0.042 mg Mn per liter, respectively,
for the control, 1-inch and 2-inch wastewater areas.
Although boron was always present in the wastewater at concentrations
below the U.S.P.H.S. recommended limit for drinking water it was of
particular interest because of its essentiality for plant growth and
the narrow range in concentration between essentiality and toxicity
which for some crops may be only a difference of 0.5 mg B per liter.
Boron concentration in the wastewater has been remarkably constant over
the years. The mean annual concentration has ranged from 0.29 to 0.42
mg B per liter. Even this low concentration has been decreased sub-
stantially in passing through the soil (Table 81). Concentration at
the 48-inch depth in the wastewater areas has ranged from only 0.041 to
0.151 mg B per liter. However even these low values represent a highly
significant increase in boron relative to the control area which ranged
from 0.018 to 0.038 mg B per liter at the 48-inch depth. In most cases
the 2-inch treatment resulted in higher concentrations than the 1-inch
treatment. The depth effect was inconsistent in the control area but
concentration fairly consistently decreased with depth in the waste-
water treated areas. The years effect (Table 95) has been inconsistent
on the control and 1-inch areas but concentrations have increased with
time on the 2-inch area. In any event, concentrations of boron recharg-
ing to the groundwater should not constitute a health hazard.
r
The slightly alkaline nature of the wastewater, with a mean annual
range from pH 7.2 to pH 8.0, would be expected to be diminished in
passing through the slightly acid to moderately acid soil profile and
such was found to be the case. The highly significant depth effect
over all treatments and years summarized in Table 82 is a reflection
of the soil profile pH pattern. The only consistent years effect
(Table 96) appears to be with the 1-inch wastewater treatment at the
6 and 24-inch depths and involves a decrease in pH with time. This
may be due in part to the diminishing hydraulic load, and hence alka-
line load, with time in the 1965-69 period on the corn rotation area.
The hydraulic load ranged from 29 inches in 1965, 32 inches in 1966,
26 inches in 1967, 20 inches in 1968 to 16 inches in 1969, As a
result the inherently acid soil has been able to acidify the percolat-
ing wastewater to a greater degree and the mean annual value includes
a relatively larger number of samples obtained during the non-
irrigation period when slightly acid, poorly buffered rainwater was
percolating through the soil.
163
-------
The MBAS (methylene blue active substance) as a measure of detergent
residual is not particularly important from a water quality stand-
point at its present levels in the wastewater. The mean annual con-
centration has decreased from 3.2 mg MBAS equivalent per liter in 1963
to as low as 0.3 in 1967. The mean annual concentration in the 1965-69
period has been 0.55 mg MBAS equivalent per liter in the wastewater.
The mean annual concentration in the soil water at the 48-inch depth
in this same period has been 0.043 mg/1 in the control area, 0.048 in
the 1-inch and 0.068 in the 2-inch wastewater area. Since the control
area has not received any detergent if one deducts its MBAS equivalent
value from that of the wastewater treated areas the values of MBAS on
the wastewater areas become even more insignificant from a water
quality standpoint. The data in Tables 83 and 97 merely emphasize the
diminishing importance of the surfactant component of detergents in
water quality since the detergent industry changed over from branched-
chain ABS to linear-chain LAS in 1965.
Since there were no comparable control suction lysimeter data for the
reed canarygrass area, comparisons will be made with the 2-inch corn
rotation area. Keeping in mind that the reed canarygrass area was
first irrigated in 1964 as compared to 1963 for the corn rotation area,
by the end of 1969 the reed canarygrass which has been irrigated year
round received 486 inches of wastewater whereas the 2-inch corn rota-
tion area with only growing season irrigation had received 360 inches
of wastewater. In spite of the larger hydraulic and chemical load on
the reed canarygrass area, if one looks at the water quality at the
48-inch depth in 1969 as shown in Figure 51 it is obvious that water
with smaller concentrations of everything except manganese, chloride
and potassium are being recharged through that area. However the only
constituent which exceeds the U.S.P.H.S. drinking water recommended
limits is manganese which was 0.22 mg Mn per liter or more than four
times the limit of 0.05 mg Mn per liter. The value on the corn rota-
tion area was only 0.038 mg Mn per liter. A possible explanation of
the high Mn level is that the greater wetness is contributing to a
higher degree of anaerobiosis and hence keeping more Mn in the more
soluble divalent form. This higher degree of anaerobiosis has prob-
ably also contributed to denitrifying some of the nitrate and in
helping to keep the nitrate concentration so desirably low.
The relatively high Mn levels at the 48-inch depth would not be
expected to persist at greater depth as one approaches the limestone
bedrock and the pH increases from values of approximately 5.2 at the
48-inch depth to values greater than 7.0. A pH difference of two units
could result in a ten thousand fold decrease in solubility if based
solely on solubility product relations for manganese hydroxide. It
is highly probable that adsorption reactions would attenuate the
manganese concentration even before the soil solution encountered
zones of higher pH. Hence it is highly unlikely that undesirable
amounts of manganese would reach the groundwater.
164
-------
25(0.25
t/i
•H Reed Canarygrass
I I Corn rotation
K Ca Mg Na
Chemical Constituents
Cl
Mn
B
PH
Figure 51. Mean Annual Concentration of Various Chemical Constituents in Suction Lysiraeter Samples
at the 48-Inch Depth in the Reed Canarygrass and Corn Rotation Areas in 1969.
-------
Table 71. Mean Annual Concentration (mg/1) of Phosphorus in Suction Lysimeter Samples at Three
Depths' in Corn Rotation Area Receiving Various Levels of Wastewater. 1965-1969.
O\
ON
Depth
Inches
6
24
48
0
0
0
0
. 035a*4/
.025a**
.032b**
1965
1
0.047a
0.021a
0.016a
1968
Wastewater
6
24
48
0
0
0
0
.039a**
.051N.S.
.043N.S.
1
0.164a
0.065
0.052
1966 1967
Wastewater Application - Inches Per Week
0.
0.
0.
2
118b
045b
022ab
0
0.044a**
0.046N.S
0.045b*
0.
. 0.
0.
1
079a
036
028a
0
0
0
2
.271b
.055
.036ab
012
0.046a** 0.159a 0.662b
0.040a** 0.039a 0.089b
0.040a** 0.030a 0.055b
1969
Application
0.
0.
0.
2
586b
080
061
- Inches
0
0.024a**
0.084N.S
0.069N.S
Per
0.
. 0.
. 0.
Week
1
073a
048
067
0
0
0
2
.603b
.062
.072
— The Duncan's separations are between wastewater treatments within depths and within years.
** « P(0.01), * = P(0.05), N.S. = not significant
-------
Table. 72. Mean Annual Concentration (mg/1) of Nitrate Nitrogen in Suction Lysimeter Samples at
Three Depths in Com Rotation Area Receiving Various Levels of Wastewater. 1965-1969,
Depth
Inches
6
24
48
6
24
48
0
6.8N.S
6.1N.S
5.3a**
0
12.6N.S
2.7a**
4.3a**
1965
1
.-/ 4.2
6.7"
8.2b
1968
Wastewater
1
. 12.0
4.5b
5.8b
1966
Wastewater Application - Inches Per.
2
4.7
7.7
9.7c
-
Application
2 •
10.5
10. 6c
9.6c
0
4.6b**
3.3b**
4. 7a**
- Inches
0
15.9N.S.
10. 5b**
9.4b**
I
1.7a
1.8a
4.9a
1969
Per leek
1
11.9
5.5a
7.7a
2
S.Ob
4.1b
7. Ob
2
18.2
14. 2c
14. Oc
1967
Week
012
l.la** 2.4b 5.2c
3.1b** 2.2a 6.6c
3.4a** 3.8a 7.1b
— The Duncan's separations are between wastewater treatments within depths and within years.
** - P(0.01), * = P(0.05), N.S. = not significant
-------
Table 73. Mean Annual Concentration (mg/1) of Kjeldahl Nitrogen-' in Suction Lysimeter Samples at
Three Depths in Com Rotation Area Receiving Various Levels of Wastewater. 1965-1969.
Depth
Inches
6
24
48
1965
1966
1967
Wastewater Application - Inches Per Week
0
-
0.97
0.68
1
0.74
0.84
0.85
2
—
0.76
0.77
0
1.08
1.46
1.30
1
2.14
1.34
1.23
2
1.69
1.57
1.40
0
1.46
1.49
1.45
1
2.17
1.59
1.55
2
1.79
1.45
1.54
1968 1969
t-»
gj Wastewater Application - Inches Per Week
012 0 1
6
24
48
0.98N.S.~y
1.06N.S.
1.27N.S.
' 1.74
0.98
1.03
1.71
1.16-
1,00
1.94N.S.
1.09N.S.
1.34N.S.
2.73
1.66
1.45
3.48
1.60
1.59
— Kjeldahl nitrogen, includes organic and ammonium nitrogen. Values for 1965, 1966, 1967 are low
by an unknown amount because of an error in procedure and were not analyzed statistically.
2/
— The Duncan's separations are between wastewater treatments within depths and within years.
** •
-------
O\
Table 74. Mean Annual Concentration (mg/1) of Ammonium Nitrogen in Suction Lysimeter Samples at ,
Three Depths in Corn Rotation Area Receiving Various Levels of Wastewater. 1968-1969—'
Depth
Inches
6
24
48
0
2/
2.72N.S.-7
0.36N.S.
O'.SON.S.
1968 1969
Wastewater Application - Inches Per Week
12 01
0.60
0.48
0.51
0.52
0.45
0.41
0.74N.S.
0.68N.S.
0.84N.S.
1.02
0.77
0.75
2
1.08
0.61
0.78
— Ammonium nitrogen was not determined separately from Kjeldahl nitrogen prior to 1968.
2/
— The Duncan's separations are between wastewater treatments within depths and within years.
** = P(0.01), * = PC0.05), N.S. = not significant
-------
Table 75. Mean Annual Concentration (mg/1) of Potassium in Suction Lysimeter Samples at Three
Depths in Corn Rotation Area Receiving Various Levels of Wastewater. 1965-1969.
Depth
Inches
6
24
48
6
24
48
0
8.15N.S
10.83b**
9.01N.S
0
1.99N.S
0.96a*
2.34a*
1964
1
.i/ 16.69
9.48b
8.07
1968
Wastewater
1
. 4.33
3.03b
2.75a
Wastewater
2
16.13
8.18a
8.79
Application
2
4.05
2.48b
3.95b
1966 1967
Application - Inches Per Week
0
5.57N.S.
5.58N.S.
5.9lab**
- Inches
0
2.47N.S.
2.43N.S.
5.35b*
1
7.61
5.95
5.36a
1969
Per Week
1
5.40
3.17
2.83a
2
7.75
5.71
6.26b
2
4.91
3.09
3.73ab
012
6.39N.S. 7.14 8.63
5.63N.S. 5.52 5.83
6.04ab* 5.20a 6.25b
— The Duncan's separations are between wastewater treatments within depths and within years.
** = P(0.01), * = P(0.05), N.S. - not significant
-------
Table 76. Mean Annual Concentration (mg/1) of Calcium in Suction Lysimeter Samples at Three Depths
in Corn Rotation Area Receiving Various Levels of Wastewater. 1965-1969.
Depth
Inches
6
24
48
1965
1966
Wastewater Application - Inches Per
61.
13.
7.
0
lON.S.i/
96a**
07a**
1
43.70
25.37c
11.71b
2
40.18
21.73b
11.76b
0
31. SON. S.
13.26a**
8.04a**
1
38.71
13.18a
7.71a
2
41.77
16.40b
9.44b
Week
26
15
6
0
. 20a**
,05b**
.29ab**
1967
1
23.20a
9.32a
5.38a
2
32.73b
14.90b
6.76b
1968
1969
Wastewater Application - Inches Per Week
12 01
6
24
48
36.25b**
11.68a**
10.13b**
24.29a
8.76a
5.72a
21.14a
16.01b
6.67a
41.05N.S.
18.23b**
14.86b**
30.89
9.53a
6.05a
30.13
19.43b
8.26a
— The Duncan's separations are between wastewater treatments within depths and within years.
** = P(0.01), * = P(0.05), N.S. = not significant
-------
NS
Table 77. Mean Annual Concentration (mg/1) of Magnesium in Suction Lysimeter Samples at Three
Depths in Corn Rotation Area Receiving Various Levels of Wastewater. 1965-1969.
Depth
Inches
6
24
48
6
24
48
0
4.15a*i'
3.99a**
2.44a**
0
1.80a**
2.26a**
3. 20a**
1965
1
' 4.61a
5.55b
4.85b
1968
Wastewater
1
4.00b
2.44a
2.80a
1966 1967
Wastewater Application - Inches Per Week
2
5.85b
4.70a
7.04c
Application
2
S.OTb
3.52b
4.43b
0
2.57N.S.
2.96a**
3.38a**
- Inches
0
1.68a**
2.76a**
3.40b**
1
9.67
3.66b
3.41a
1969
Per Week
1
5. lib
2.28a
2.65a
2
6.52
3.48b
5.53b
2
8.73c
4.32b
4.82c
012
2.07a** 4.17b 5.65c
1.86a** 2.62b 3.13c
2.44a** 2.70a 4.86b
— The Duncan's separations are between wastewater treatments within depths and within years.
** = P(0.01), * = P(0.05), N.S* « not significant
-------
Table 78. Mean Annual Concentration (mg/1) of Sodium in Suction Lysimeter Samples at Three Depths
in Corn Rotation Area Receiving Various Levels of Wastewater. 1965-1969.
Depth
Inches
6
24
48
0
2.25a**i/
2.89a**
2.03a**
1965
1
35.89b
27.17b
19.06b
Wastewater
2
45.05c
30.02c
27.16c
1.
2.
2.
1966
Application - Inches Per Week
0 12
29a**
59a**
85a**
37.10b
26.80b
20.29b
38.22b
34.59c
29.43c
2
1
1
0
.Ola**
.49a**
.57a**
1967
1
34.84b
28.74b
23.77b
2
31.24b
35.06c
31.01c
1968
1969
Wastewater Application - Inches Per Week
012 01
6
24
48
l.lOa**
1.62a**
2.72a**
29.57b
25.14b
21.80b
26.40b
30.12c
28.79c
1.03a**
1.48a**
1.79a**
31.66b
26.56b
22.95b
35.01b
37.64c
32.28c
— The Duncan's separations are between wastewater treatments within depths and within years,
** = P(O.Ol), * = P(0.05), N.S. - not significant
-------
Table 79. Mean Annual Concentration (mg/1) of Chloride in Suction Lysimeter Samples at Three
Depths in Com Rotation Area Receiving Various Levels of Wastewater. 1965-1969.
Depth
Inches
6
24
48
0
33. Sa**^
10. 3a**
5.6a**
1965
1
40. Ib
43. 2c
25. 7b
1966
Wastewater Application - Inches Per Week
2 012 0
39. 2a
38. 5b
35. 3c
8.8a**
10. 9a**
8.8a**
49. 3c
46. 7c
31. 7b
41. 5b
43. 9b
40. 3c
1.4a**
7.9a**
5.2a**
1967
1
21. 6b
30. 7b
28. 3b
2
28. 4c
31. 5b
35. 6c
1968 1969
Wastewater Application - Inches Per Week
12 01
6
24
48
8.2a**
5.4a**
6.3a**
30. 5b
29. Ob
28. 5b
31. Ib
32. Oc
34. 6c
3.9a**
4.5a**
4.8a**
27. Ib
25. 2b
26. 4b
31. 9b
27. 6b
32. 7c
— The Duncan's separations are between wastewater treatments within depths and within years.
** = P(0.01), * = P(0.05), N.S. - not significant
-------
en
Table 80. Mean Annual Concentration (mg/1) of Manganese in Suction Lysimeter Samples at Three
Depths in Corn Rotation Area Receiving Various Levels of Wastewater. 1965-1969.
Depth
Inches
6
24
48
6
24
48
0
0
0
0
0
0
0
.040N.S.
.067N.S.
.lOOb*
0
.023N.S.
.028N.S.
.105c**
1965
1
If 0.033
0.056
0.066b
1968
Wastewater
1
0.017
0.024
0.062b
Wastewater
0
0
2
«
.035
.047a
0
0
0
Application -
0
0
0
2
.015
.022
.027a
0
0
0
1966 1967
Application - Inches Per Week
0
.036N.S.
.OSSb**
.072c**
Inches
0
.084N.S.
.087b**
.069b**
1
0.035
0.058b
0.060b
1969
Per Week
1
0.024
0.026a
0.041a
0
0
0
0
0
0
2
.030
.042a
.052a
2
.028
.030a
.038a
0 12
0.041N.S. 0.035 0.041
0.042b** 0.049b 0.031a
0.053a** 0.071b 0.044a
—' The Duncan's separations are between wastewater treatments within depths and within years.
P(0.01), * = P(0.05), N.S. - riot significant
**
-------
Table 81. Mean Annual Concentration (mg/1) of Boron in Suction Lysimeter Samples at Three Depths
in Corn Rotation Area Receiving Various Levels of Wastewater. 1965-1969.
1965
Depth
Inches
6
24
48
0
0.015 17
0.030a**i'
0.030a**
1
0.140
0.046a
0.041a
Wastewater
2
0.085b
0.066b
0
0
0
1966
1967
Application - Inches Per Week
0
.047a**
.039a**
.038a**
1
0.164b
0.070b
O.OSSb
2
0.221c
0.147c
0.097c
0.
0.
0.
0
051a**
034a**
029a**
1
0.265b
0.082b
0.065b
2
0.310b
0.198c
0.127c
CTi
1968
1969
Wastewater Application - Inches Per Week
12 01
6
24
48
0.024a**
0.021a**
O.OlSa**
0.194b
0.068b
0.056b
0.253b
0.184c
0.116c
0.027a**
O.OlSa**
0.031a**
0.236b
0.060a
0.063b
0.242b
0.212b
O.lSlc
— The Duncan's separations are between wastewater treatments within depths and within years.
** = P(0.01), * = P(0.05), N.S. = not significant
-------
Table 82. Mean Annual pH in Suction Lysimeter Samples at Three Depths in Corn Rotation Area
Receiving Various Levels of Wastewater. 1965-1969.
Depth
Inches
6
24
48
6.
6.
6.
0
9a**!/
6a**
5b**
1965
1
7.6c
6.8c
6.4a
1968
1966
Wastewater Application -
2
7.5b
6.7b
6.5b
0
6.9a**
6.5a**
6.3a**
1
7.4b
6.7b
6.4a
1969
Wastewater Application -
6
24
48
6.
6.
6.
0
6a**
3a**
Oa**
1
7. Ob
6.6b
6.3b
2
7.3c
6.9c
6.6c
0
6.8a**
6.5a**
6.2a
1
6.9a
6.5a
6.4b
Inches
2
7.4b
6.8b
6.6b
Per Week
0
7.0a**
6.4a**
6. la**
1967
1
7.4b
6.7b
6.2b
-
2
7.4b
6.8c
6.5c
1965-1969
Inches
2
7.4b
6.8b
6.6c
Per Week
0
6.9cl/
6.5b
6.3a
1
7.3c
6.7b
6.4a
2
7.4c
6.8b
6.6a
Ave.
7.2c
6.7b
6.4a
— The Duncan's separations are between wastewater treatments within depths and within years.
** - P(0.01), * = P(0.05), N.S. = not significant
21
— Values in the same column not having a common letter are different at a highly significant
level (P = 0.01) using Duncan's range test.
-------
c»
Table 83. Mean Annual Concentration (mg/1) of MBAS in Suction Lysimeter Samples at Three Depths
in Com Rotation Area Receiving Various Levels of Wastewater. 1965-1969.
Depth
Inches
6
24
48
6
24
48
0
0
0
0
0
0
0
• \J £t i d
.008a**
.009a**
0
.055N.S.
.043N.S.
.049N.S.
1965
I
I 0.048b
0.034b
0.026b
1968
Wastewater
1
0.036
0.048
0.048
Wastewater
0.
0.
0.
2
066c
053c
06 Oc
0
0
0
Application -
0.
0.
0.
2
068
040
049
0
0
0
1966 1967
Application - Inches Per Week
0
.040N.S.
.016a**
.017a**
Inches
0
.067
.070N.S.
.085N.S.
1
0.042
O.OSOb
0.023a
1969
Per Week
1
_
0.042
0.079
0.
0.
0.
0.
0.
2
047
040c
040b
2
_
041
115
0 12
0.044a** O.OSlb 0.077b
0.043a** 0.063b 0.069b
0.056a* 0.063a 0.075b
—' The Duncan's separations are between wastewater treatments within depths and within years.
** = P(0.01), * = P(0.05), N.S. = not significant
-------
Table 84. Mean Annual Concentration (mg/1) of Various Constituents in Suction Lysimeter Samples
at Three Depths in the Reed Canarygrass Area Receiving Two Inches of Wastewater Weekly.
1966-1969.
1966 1967 1968 1969
Constituent 6" 24" 48" 6" 24" 48" 6" 24" 48" 6" 24" 48"
Phosphorus 0,165 0.095 0.060 0.135 0.105 0.055 0.220 0.105 0.060 0.205 0.195 0.030
MBAS 0.025 0.025 0.015 0.045 0.055 0.055 0.145 0.050 0.050 0.060 0.063 0.063
Nitrate-N 0.8 2.3 3.9 0.5 1.3 3.3 0.5 1.5 3.2 0.6 1.0 2.7
Organic and
Ammoniacal-N t 1.4 1.4 2.2 1.8 1.5 2.8 1.4 1.2 3.0 3.5 2.4
Chloride 39.4 40.2 24.8 31.0 34.6 27.6 24.4 33.6 31.5 36.6 40.0 38.3
Potassium 6.0 6.5 6.2 7.2 6.2 7.1 5.4 3.0 3.3 8.4 5.9 4.2
Calcium 7.7 15.9 7.3 16.4 14.0 6.1 24.5 11.4 5.4 32.4 12.2 4.8
Magnesium 2.9 5.2 3.6 4.2 3.6 2.8 4.8 2.9 3.0 6.4 3.4 2.6
Manganese 0.27 0.61 0.68 0.27 0.29 0.34 0.05 0.26 0.25 0.44 0.19 0.22
Boron 0.06 0.09 0.06 0.23 0.17 0.08 0.29 0.19 0.07 0.34 0.23 0.09
Sodium 17.2 26.7 16.3 32.1 30.2 22.2 37.5 28.7 22.2 31.3 30.9 24.4
pH 7.4 6.7 6.5 7.3 6.8 6.5 7.3 6.9 6.6 7.4 6.8 6.5
t Not Determined
-------
Table 85. The Effect of Years on Mean Annual Concentration (mg/1) of
Phosphorus in Suction Lysimeter Samples at Three Depths in
the Corn Rotation Area Segregated by Wastewater Treatment
Level. 1965-1969.
Depth
Inches
6
24
48
6
24
48
6
24
48
1965
0.035
0.025a
0.032a
0.047a
0.021a
0.016a
O.llSa
0.045a
0.022a
1966
0
0.044
0.046a
0.045a
1
0.079a
0.036b
0.028b
2
0.271b
O.OSSa
0.036b
1967
inch/week
0.046
0.040a
0.040a
inch/week
0.159b
0.039b
0.030b
1968
0.039
O.OSlab
0.043a
0.164b
0.065c
0.052c
1969
0.024
0.084b
0.069b
0.073a
0.048bc
0.067d
N.S.1/
it
ft
ft*
**
ft*
inches/week
0.662c
0.089c
O.OSSc
0.586c
O.OSObc
0.061c
0.603c
0.062ab
Q.072c
ft*
ft*
ft*
— The Duncan's separations are between years within depths and within
wastewater treatments. ** = P(0.01), *•- P(0.05), N.S. not signifi-
cant
180
-------
Table 86. The Effect of Years on Mean Annual Concentration (mg/1) of
Nitrate Nitrogen in Suction Lysimeter Samples at Three
Depths in the Corn Rotation Area Segregated by Wastewater
Treatment Level. 1965-1969.
Depth
Inches 1965 1966 1967 1968 1969
0 inch/week
6 6.8b 4.6b l.la 12.6c 15.9c
24 6.1b 3.3a 3. la 2.7a 10.5c **
48 5.3b 4.7b 3.4a 4.3ab 9.3c **
1 inch/week
6
24
48
4.2b
6.7c
8.2d
1.7a
1.8a
4.9b
2.4a
2.2a
3.8a
12. Oc
4.6b
5.8c
11. 9c
5.5bc
7.7d
**
**
**
2 inches/week
6
24
48
4.7a
7.7b
9.7b
S.Oa
4. la
7.0a
5.2a
6.6b
7. la
10. 5b
10. 7c
9.6b
18. 2c
14. 2d
14. Oc
**
**
**
—' The Duncan's separations are between years within depths and within
wastewater treatments. ** - P(0.01), * - P(0.05), N.S. • not
significant
181
-------
Table 87. The Effect of Years on Mean Annual Concentration (mg/1) of
Kjeldahl Nitrogen in Suction Lysimeter Samples at Three
Depths in the Corn Rotation Area Segregated by Wastewater
Treatment Level. 1965-1969.!'
Depth
Inches
1965
1966
1967
1968
1969
6
24
48
6
24
48
0.97
0.68
0.74
0.84
0.85
0 inch/week
1.08 1.46 0.98
1.46 1.49 1.06
1.30 1.45 1.27
1 inch/week
2.14 2.17 1.74
1.34 1.59 0.98
1.23 1.55 1.03
2 inches/week
1.94
1.09
1.34
2.73
1.66
1.45
6
24
48
0.30
0.76
0.77
1.69
1.57
1.40
1.79
1.45
1.54
1.71
1.16
1.00
3.48
1.60
1.59
--' Error in procedure resulted in losses of unknown amounts of ammonium
nitrogen in 1965, 1966 and 1967 therefore statistical treatment was
not attempted.
182
-------
Table 88. The Effect of Years of Mean Annual Concentration (mg/1) of
Ammonium Nitrogen in Suction Lysimeter Samples at Three
Depths in the Corn Rotation Area Segregated by Wastewater
Treatment Level. 1968-1969.1/
Depth
Inches 1968 1969
0 inch/week
6 2.72 0.74
24 0.36 0.68
48 0.50 0.84
1 inch/week
6 0.60 1.02
24 0.48 0.77
48 0.51 0.75
2 inches/week
6 0.52 1.08
24 0.45 0.61
48 0.41 0.78
— Separate determination of ammonium nitrogen was not made prior to
1968. Test for significance not attempted.
183
-------
Table 89. The Effect of Years on Mean Annual Concentration (mg/1) of
Potassium in Suction Lysimeter Samples at Three Depths in
the Corn Rotation Area Segregated by Wastewater Treatment
Level. 1965-1969.
Depth
Inches
6
24
48
6
24
48
6
24
48
1965
8.15b
10.83c
9.01c
16.69b
9.48c
8.07c
16.13c
8.18c
8.79c
1966
5.57ab
5.58b
5.91b
7.61a
5.95b
5.36b
7. 75ab
5.71b
6.26b
1967 1968
0 inch/week
6.39b 1.99a
5.63b 0.96a
6.04b 2.34a
1 inch/week
7.14a 4.33a
5.52b 3.03a
5.20b 2.75a
2 inches/week
8.63b 4.05a
5.83b 2.48a
6.25b 3.95a
1969
2.47a **_/
2.43a **
5.35b **
5.40a **
3.17a **
2.83a **
4.91a **
3.09a **
3. 73a **
— The Duncan's separations are between years within depths and within
wastewater treatments. ** = P(0.01), * = P(0.05), N.S. = not
significant
184
-------
Table 90. The Effect of Years CHI Mean Annual Concentration (mg/1) of
Calcium in Suction Lysimeter Samples at Three Depths in
the Corn" Rotation Area Segregated by Wastewater Treatment
Level. 1965-1969.
D»pth
Inches
1965 1966 1967 1968
1969
0 inch/week
6 61.10C 31.3Qab 26.20a 36.25ab 41.05b
24 13.96 13.26 15.05 11.68 18.23 N.S.
48 7.07ab 8.04ab 6.29a 10.13b 14.86c **
1 inch/week
6 43.70b 38.71b 23.20a 24.29a 30.89ab **
24 25.37b 13.1§a 9.32a 8.76a 9.53a **
48 U.71c 7.71b 5.38a 5.72a 6.05ab **
2 inches/week
6 40.18b 41.77b 32.73b 21.14a 30.13b **
24 21.73b 16,40a 14.90a 16.Ola 19.43b **
48 11.76C 9.44b 6.76a 6.67a 8.26ab **
* &
a Ihe Duncan's separations are between years within depths and within
wastewater treatments. ** • P(0.01), * = P(0.05), N.S. = not
significant
185
-------
Table 91. The Effect of Years on Mean Annual Concentration (mg/1) of
Magnesium in Suction Lysimeter Samples at Three Depths in
the Corn Rotation Area Segregated by Wastewater Treatment
Level. 1965-1969.
Depth
Inches
6
24
48
1965
4.15b
3.99c
2.44a
1966
2.57a
2.96b
3.38b
1967
0 inch/week
2.07a
1.86a
2.44a
1968
l.SOa
2 . 26ab
3.20ab
1969
1.68a
2.76b
3.40b
**!/
**
**
1 inch/week
6 4.61 9.67. 4.17 4.00 5.11 N.S.
24 5.55c 3.66b • 2.62a 2.44a 2.28a **
48 4.85c 3.41b 2.70a 2.8pa 2.65a **
2 inches/week
6
24
48
5.85a
4. 70b
7.04c
6.52a
3.48a
5.53b
5.65a
3.13a
4.86ab
5.07a
3.52a
4.43a
8.73b
4.32b
4.82ab
A*
**
**
— The Duncan's separations are between years within depths and within
. wastewater treatments. ** = P(0.01), * = P(0.05), N.S. = not
significant
186
-------
Table 92. The Effect of Years on Mean Annual Concentration (mg/1) of
Sodium in Suction Lysimeter Samples at Three Depths in the
Corn Rotation Area Segregated by Wastewater Treatment Level.
1965-1969.
Depth
Inches
6
24
48
1965
2.25
2.89
2.03abc
1966
1.29
2.59
2.85c
1967
0 inch/week
2.01
1.49
1.57a
1968
1.10
1.62
2.72bc
1969
1.03 N.S.i/
1.48 N.S.
1.79ab **
1 inch/week
6 35.89 37.10 34.84 29.57 31.66 N.S.
24 27.17ab 26.80ab 28.74b 25.14a 26.56ab *
48 19.06a 20.29b 23.77d 21.80c 22.95cd **
2 inches/week
6
24
48
45.05d
30.02a
27.16a
38.22cd
34.59b
29.43b
31.24b
35.06bc
31.01bc
26.40a
30.12a
28.79ab
35.01bc
37.64c
32.28c
**
**
**
— The Duncan's separations are between years within depths and within
wastewater treatments. ** = P(0.01), * = P(0.05), N.S. = not
significant
187
-------
Table 93. The Effect of Years on Mean Annual Concentration (mg/1) of
Chloride in Suction Lysimeter Samples at Three Depths in
the Com Rotation Area Segregated by Wastewater Treatment
Level. 1965-1969.
Depth
Inches
6
24
48
1965
33. 5c
10. 3c
5.6a
1966
8.8b
10. 9c
8.8b
1967
0 Inch/week
1.4a
7.9b
5.2a
1968
8.2b
5.4a
6.3a
1969
3.9ab
4.5a
4.8a •
**!/
**
it*
I inch/week
6 40.Ib 49.3b 21.6a 30.5a 27.la **
24 43.2d 46.7c 30.7b 29.0ab 25.2a **
48 25.7a 31.7c 28.3b 28.5b 26.4a **
2 inches/week
6
24
48
39. 2b
38. 5c
35. 3b
41. 5b
43. 9d
40. 3c
28. 4a
31. 5b
35. 6b
31. la
32. Ob
34. 6b
31. 9a
27. 6a
32. 7a
**
**
**
— The Duncan's separations are between years within depths and within
wastewater treatments. ** = P(0.01), * = P(0.05), N.S. = not
significant
188
-------
Table 94. The Effect of Years on Mean Annual Concentration (mg/1) of
Manganese in Suction Lysimeter Samples at Three Depths in
the Corn Rotation Area Segregated by Wastewater Treatment
Level. 1965-1969.
Depth
Inches
1965
1966
1967
1968
1969
0 inch/week
6
24
48
0
0
0
.047
.067bc
.lOObc
0.041
O.OSSb
0.072b
0
0
0
.036
-042ab
.053a
0
0
0
.023
.028a
.105c
0
0
0
.084
.087c
.069ab
N.S.i/
**
**
6
24
48
0.033
0.056bc
0.066
0.035
0.058c
0.060
1 inch/week
0.035
0.049b
0.071
0.017
0.024a
0.062
0.024
0.026a
0.041
2 inches/week
N.S.
**
N.S.
6
24
48
_
0.035bc
0,047bc
0.030ab
0.042c
0.052c
0.041b
0.031b
0.044b
O.OlSa
0.022a
0.027a
0.028ab
0.030ab
0.038ab
A*
**
**
— The Duncan's separations are between years within depths and within
wastewater treatments. ** = P(0.01), * = P(0.05), N.S. = not
significant
189
-------
Table 95. The Effect of Years on Mean Annual Concentration (mg/1) of
Boron in Suction Lysimeter Samples at Three Depths in the
Corn Rotation Area Segregated by Wastewater Treatment
Level. 1965-1969.
Depth
Inches
6
24
48
0
1965
.OlSa
O.OSOab
0
.030b
1966
0.
0.
0.
0
047ab
039b
038c
1967
1968
1969
inch/week
0
0
0
.OSlb
.034b
.029b
0
0
0
.024a
.021a
.018a
0
0
0
.027a
.018a
.031bc
**!/
**
**
6
24
48
0.140
0.046a
0.041
0.164
0.070bc
0.058
1 inch/week
0.265
0,082c
0.065
0.194
0.068abc
0.056
0.236
0.060ab
0.063
2 inches/week
N.S.
ft*
N.S.
6
24
48
-
0.085a
0.066a
0.221a
0.147b
0.097b
0.310b
0.198c
0.127c
0.253a
0.184c
0.116c
0.242a
0.212c
O.lSld
*
**
**
— The Duncan's separations are between years within depths and within
wastewater treatments. ** = P(0.01), * = P(0.05), N.S. = not
significant
190
-------
Table 96. The Effect of Years on Mean Annual pH in Suction Lysimeter
Samples at Three Depths in the Corn Rotation Area Segregated
by Wastewater Treatment Level. 1965-1969.
Depth
Inches
6
24
48
1965
6.9bc
6.6c
6.5c
1966
6.9bc
6.5bc
6.3b
1967
0 inch/week
7.0c
6.4b
6. la
1968
6.6a
6.3a
6.0a
1969
6. Sab
6.5bc
6.2b
**!/
*
**
1 inch/week
6 7.6c 7.4b 7.4b 7.0a 6.9a **
24 6.8c 6.6b 6.7b 6.6b 6.5a **
48 6.4b 6.4b 6.2a 6.3b 6.4b **
2 inches/week
6
24
48
7.5b
6.7a
6.5a
7.4ab
6.8b
6.6b
7.4ab
6,9b
6.5a
7.3a
6.9b
6.6b
7.4ab
6.8b
6.6b
A
ft*
**
— The Duncan's separations are between years within depths and within
wastewater treatments. ** = P(0.01), * - P(O.OS), N.S. = not
significant
191
-------
Table 97. The Effect of Years on Mean Annual Concentration (mg/1) pf
MBAS in Suction Lysimeter Samples at Three Depths in the"
Corn Rotation Area Segregated by Wastewater Treatment
Level. 1965-1969.
Depth
Inches
6
24
48
1965
0.027
O.OOSa
0.009a
1966
0.040
0.016a
0.017a
1967 1968
0 inch/week
0.044 0.055
0.043b 0.043b
0.056b 0.049b
•
1969
0.067 N.S.J/
0.070b «*
O.OSSb **
1 inch/week
6 0.048a 0.042a O.OSlb 0.036a - M
24 0.034a 0.030a 0.063b 0.048b 0.042ab »*
48 0.026a 0.023a 0.063c 0.048b 0.079e **
2 inches/week
6
24
48
0.066c
0.053b
0.060b
0.047b
0.040a
0.040a
0.077c
0.069b
0.075c
0.068c
0.040a
0.049ab
0.032a
0.041ab
O.llSd
**
ft*
**
1 /
— The Duncan's separations are between years within depths pid wifhin
wastewater treatments. ** = P(0.01), * * P(0.0§), N.S.
significant
192
-------
Soil Chemical Characteristics
Previous Work. The physical and chemical changes that occur in soil
through which wastewater percolates have been given less attention
than the changes occurring in the effluent itself. However, particu-
larly in the Western States, much work has been done in attempts to
classify irrigation waters on the bases of relative as well as total
ionic concentration. Scofield and Headley (49) found that a pre-
dominance of sodium in irrigation water caused a decrease in aggrega-
tion of the soil and a reduction in the rate of infiltration of
water. Where calcium was the major cation just the opposite was
found to be true. They concluded that for water to be acceptable for
irrigation, the ratio of sodium to calcium plus magnesium should not
exceed 1:1.
Kelly et al. (50) investigated the effects of relative ionic composi-
tion ami total concentration of ions in solution on the suite of ions
borne by the exchange complex of the soil. They found that the
adsorption of sodium by the soil from a sodium-calcium solution
increased with an increase in the ratio of sodium to calcium and with
an increase in the total ionic concentration. Above a sodium:calcium
ratio of 2:1, sodium was adsorbed in significant amounts by the soil.
However, the adsorption of sodium was influenced by the kind of base
held by the soil and was lower when calcium was present on the exchange
complex than when magnesium was present. The results were attributed
to the differential replacing power of these bases as previously
measured (51). It was also found that the adsorption of sodium by
the soil from a sodium-calcium solution was due largely to the replace-
ment of magnesium. On the other hand, tests with solutions containing
various ratios of sodium to calcium plus magnesium showed that the
sodium was adsorbed by the soil mainly at the expense of calcium.
Evidence cited by the authors indicated that because of evapotranspir-
ation, the concentration of the soil solution could undergo a six-fold
increase compared to the concentration of the irrigation water. In
such a situation, the removal of calcium from solution either by
precipitation or by root uptake could result in an unfavorable relative
concentration of sodium and, consequently, adsorption of sodium by the
soil. The authors, therefore, have recommended that the ratio of
sodium to calcium plus magnesium in irrigation water should not exceed
1:1 unless the total salt concentration of the water was quite low.
Wilcox (52) classified irrigation water on the bases of percentage
sodium and total cations present. The percentage sodium was determined
according to the following equation
Percentage Na = ^f X 100 ,
Ca + Mg + K + Na
where the concentrations of cations are expressed in me/A. He regarded
193
-------
the water as acceptable for irrigation of agricultural lands only if
the percentage sodium was less than 80 and if the total concentration
of cations did not exceed 25 me/£.
In 1953, the United States Regional Salinity Laboratory (53) proposed
a classification of irrigation water based on the sodium adsorption
ratio (SAR) and the total salt concentration as measured by electrical
conductivity.
Na where concentrations of the
SAR = cations are expressed in me/a
V-
(Ca + Mg)
The sodium adsorption ratio was believed to be theoretically more
closely related to the exchangeable sodium percentage (ESP) in the soil
than were the simpler sodium percentage values. Thus, irrigation water
may be considered to be of low sodium hazard if the SAR was not greater
than ten. However, in order to maintain this classification, the
maximum permissible SAR would decrease as the total salt concentration
increased.
Based on the above classifications, the quality of wastewater applied
to cropland, while not excellent in every respect, has usually not had
any deleterious effects on the soil. Henry et al. (24) reported that
in soil that had been treated with sewage efTTuent containing 680 ppm
of sodium the concentration of exchangeable sodium amounted to 2.37
m.e./lOO grams. They also found that owing to the preponderance of
sodium in the effluent, calcium and magnesium in the soil were signifi-
cantly diminished. The exchangeable potassium was not affected by
percolation of the effluent although there was twice as much potassium
added as there was removed by the reed canarygrass being grown. They
concluded that the potassium was being fixed in a nonexchangeable form.
It is noteworthy that the authors reported no difficulty with percola-
tion during their three-year study.
In an investigation of the spreading of primary sewage effluent on
California soils (37) it was reported that calcium and magnesium in
the soil both decreased while sodium, potassium and ammonium increased.
It was also noted that although the ratio of monovalent cations to the
total cations in the effluent was 0.641, permeability of the soil was
not affected probably because of the low clay content (3-10 percent).
In general the surface soil showed the greatest exchange between
monovalent and divalent ions but there was no significant correlation
with depth.
In Israel, Heukelekian (25) reported that plots irrigated at rates of
20-30 inches per year with sewage effluent showed an accumulation of
salts, especially chlorides, and these were concentrated in the upper
layers of the soil. During the rainy season, the salts were removed
194
-------
by leaching and the soil returned to its pre- irrigation levels with
respect to salt content. Gradual increases in organic matter were
also observed in the surface layers of the irrigated plots.
The general preoccupation with exchangeable sodium stems from the well
documented research in irrigation agriculture which has shown that
when the exchangeable sodium percentage reaches a value of 10 to 15 a
deterioration of soil structure and adverse effects on infiltration
can be expected in medium and fine textured soils.
Exchangeable Cations. Soil samples were taken by one-foot intervals
at 21 locations in each wastewater treatment area in 1963, 1965, 1966,
1967, 1968 and 1969 in the corn rotation area. In the reed canary-
grass area sampling at the same depth intervals was done at 18 loca-
tions in 1969. In the Game lands hardwood forest area samples were
taken in 1967 from nine locations in the wastewater area and from
three locations in the control area.
The exchangeable bases were extracted with normal ammonium acetate at
pH 7.0; the exchangeable hydrogen with barium chloride-triethanolamine
at pH 8. Details of the soil analytical procedures are given in the
Appendix. The exchangeable cation data and other chemical data are
given in Tables 98 to 105 on pages 205 to 212.
Summarized over the five soil depths and six years, Figure 52 indicates
that in the corn rotation area there was a significant change due to
wastewater treatment only in the case of exchangeable magnesium and
sodium. Figure 53 indicates that the relative increase in exchangeable
magnesium due to wastewater application was greatest in the upper foot.
Below the second foot increases were greater with the 1-inch per week
application than with the 2-inch per week treatment. In the third and
fifth foot the 2-inch treatment was significantly different from the
control (0-inch) only at the 5% level of probability. In the fourth
foot the 2-inch treatment value was not significantly greater than the
control.
Figure 54 indicates that exchangeable sodium increases were also
greatest in the upper foot and it appears that both the one and two
inch per week treatments have peaked at a value of approximately 0.5
m.e./lOO grams of soil, equivalent to an ESP value of approximately
2.5 to 3.0%. Thus it appears highly probable that with the present
wastewater quality, with an SAR value less than 2.0, one need not be
concerned about a sodium hazard to soil structure and permeability.
With respect to the other principal exchangeable cations, K, Ca and H,
there were no significant treatment effects when averaged over depths
and years (Figure 52) or within depths over years. Since the area had
been limed during the previous farm management program, a sharp
decrease of Ca with depth was present originally and this depth effect
has persisted.
195
-------
10
to
o\
8
O 4
o
0
E 2
iiil I inch per week
2 inches per week
Mg K No
Exchangeable Cations
H
Figure 52. Effect of Various Wastewater Levels on the Corn Rotation Area on Exchangeable Cations
Averaged Over Five One-Fbot Depth Intervals and Over Six Sampling Years, 1963, 1965-
1969. Bars Having a Common Letter far Any Constituent Are Not Significantly Different.
p = 0.01
-------
1.5 _
§ 1.0
0)
a.
a>
6 0.5
waste water levels:
I I 0 inch per week • 2 inches per week
I inch per week
c
12345
soil depth - ft.
Figure 53. Exchangeable Magnesium at One-Foot Depth Intervals in the Corn Rotation Area Averaged
Over Six Sampling Years, 1963, 1965-1969. Bars Having a Common Letter at Any Depth
Are Not Significantly Different. P = 0.01
-------
to
oo
wostewoter levels:
0 inch per week
I inch per week
2 inches per week
soil depth - ft.
Figure 54. Exchangeable Sodium at One-Foot Depth Intervals in the Corn Rotation Area Averaged
Over Six Sampling Years, 1963, 1965-1969. Bars Having a Common Letter at Any Depth
Are Not Significantly Different. P - 0.01
-------
The small increases in exchangeable Mg and Na were reflected in an
increase in base saturation which in turn was reflected in a signifi-
cant increase in pH in the upper two feet of soil for both the 1-inch
and 2-inch treatments (Figure 55).
Although manganese Obi) is not commonly measured among the exchangeable
cations because it is usually present only in small amounts, it was
included in this study because of the possible effect of the increased
wetness in increasing the solubility of Mn by oxidation-reduction
reactions. The data in Figure 56 indicate that differences due to
wastewater treatments were not significant in the more aerobic and
less acid upper two feet of soil but were highly significant (P = 0.01)
for the one-inch treatment and significant (P = 0.05) for the 2-inch
treatment in the lower three feet. KLausner (54) in aeration studies
in the corn rotation area found a slightly lower mean oxygen diffusion
rate in the 1-inch and 2-inch treatment areas. As a consequence of
diminished availability of oxygen, the higher oxides of manganese,
which are visible in the soil as black coatings on structural peds,
could be reduced to divalent manganese and thereby become more soluble
and interact with the exchange sites.
In the reed canarygrass area (Table 104) the larger hydraulic loads
have resulted in an even greater quantity of exchangeable manganese in
the second and third foot, 12.6 and 9.49 micrograms Mn per gram of
soil compared to 3.97 and 6.75 micrograms in 1969 in the 2nd and 3rd
foot of the two-inch corn rotation area. The lower oxidation status
and hence greater possibility for denitrification in the reed canary-
grass area may be responsible in part for the substantially lower
nitrate levels in that area.
Soil Chloride. Since the Hublersburg soil is known to contain sub-
stantial amounts of free iron oxides (55, 56) and such oxides have a
substantial capacity for adsorbing anions, soil samples were extracted
with 0.05N-NH4 N03 to determine the adsorbed chloride content. The
data' in Table 106 and Figure 57 show that adsorbed chloride increased
with soil depth and that the differences between the wastewater treat-
ments were not significant in the first foot where free iron oxide was
generally found to be less than 4%. However in the deeper layers where
free iron oxide ranged from 5 to 6%, adsorbed chloride in the 2-inch
treatment was highly significantly greater and in the 1-inch treatment
significantly greater than in the control for the second and third
foot. In the fourth and fifth foot differences in adsorbed chloride
were highly significant for all three wastewater treatments.
In the reed canarygrass area (Table 104) the adsorbed chloride was
uniformly high throughout the five foot depth but lower than the maxi-
mum concentrations occurring in the com rotation area. This may
reflect the wash-out equilibrium concentration of the larger hydraulic
loading on this area whereas, on the corn rotation area with a small
199
-------
O
O
6.5
6.0
I
a.
5.5
5.0
4.5
D
wostewater levels:
0 inch per week
I inch per week
2 inches per week
soil depth - ft.
Figure 55. Soil pH at One-Foot Depth Intervals in the Corn Rotation Area Averaged Over Six
Sampling Years, 1963, 1965-1969. Bars Having a Common Letter at Any Depth Are Not
Significantly Different. P = 0.01
-------
10 _
ts)
O
M
wostewater levels
I—' 0 inch per week
2 inches per week
b b
I inch per week
N.S
2345
soil depth - ft.
Figure 56. Exchangeable Manganese at One-Foot Depth Intervals in the Corn Rotation Area Averaged
Over Six Sampling Years, 1963, 1965-1969. Bars Having a Common Letter at Any Depth
Are Not Significantly Different. P = 0.01
-------
63 _
o
tsj
waste water levels:
I I 0 inch per week
I 1 I inch per week
I—I 2 inches per week
12343
soil depth - ft.
Figure 57. Extractable Chloride at One-Foot Depth Intervals in the Corn Rotation Area Averaged
-Over Six Sampling Years, 1963, 1965-1969. Bars Having a Common Letter at Any Depth
Are Not Significantly Different. P = 0.01
-------
hydraulic load combined with evaporational loss of water, the deten-
tion time of chloride in the upper five feet would be longer and the
equilibrium concentration greater and hence the adsorbed chloride
content should be greater.
Assuming a conservative 4,000,000 pounds per acre foot of soil in the
corn rotation area, the total adsorbed chloride in the 2-inch treat-
ment area for the five-foot depth was 1216 pounds per acre in 1969,
approximately 3.8 times as much as was added in the 32 inches of
wastewater applied that year. In contrast to this the Morrison sandy
loam at the Gamelands area which contains less than half as much free
iron oxide and had been treated with 208 inches of wastewater in two
years prior to sampling in 1967 had only 712 pounds of adsorbed
chloride per acre (Table 105). As with the reed canarygrass area the
larger hydraulic load on the sandy Gamelands area soil probably
resulted in an adsorbed chloride content which represents a wash-out
equilibrium concentration with an even shorter detention time in the
upper five feet than in the reed canarygrass area.
The years effect on adsorbed chloride in the com rotation area was not
consistent with time although there appeared to be a plateau in content
in the period 1966-1968. These three years each had above normal pre-
cipitation for the three months, Sept, Oct, and Nov just prior to when
the soil samples were obtained in November. In 1969 precipitation was
slightly below normal for these three months and almost four inches
below normal for the year. As a consequence adsorbed chloride was
substantially higher than in 1968. Because of the weak bonding forces
between chloride and soils, adsorbed chloride could be expected to
decrease by desorption during leaching by precipitation if application
of chlorides ceased or diminished.
Soil Boron. The ammonium acetate extract for exchangeable bases was
also analyzed for boron on the emission spectrograph and it was found
that although the extracted boron in the corn rotation area was
slightly greater in the wastewater treated plots than in the control
plots the differences were not statistically significant (Table 107).
The low concentrations in the applied wastewater (0.4mg B per liter)
would not be expected to result in a large adsorbed boron level in the
soil even though free iron and aluminum hydrated oxides have been
shown to be capable of adsorbing relatively large amounts of boron
(57). The boron relations will be described in greater detail in a
later section summarizing the work of Jardine (55).
Soil Nitrogen and Organic Matter. Neither nitrogen nor organic matter
levels were significantly different as a result of the wastewater
treatments on the corn rotation area (Table 108). The highly signifi-
cant depth difference for both nitrogen and organic matter resides in
the large difference between the values in the first foot and the other
four feet. Between the second foot and the lower three feet the
203
-------
nitrogen values were highly significantly different (P = 0.01) but
with the organic matter values the differences were only significantly
different (P = 0.05). In 1968 the five foot depth of soil contained
8120, 7840 and 7760 pounds of nitrogen per acre, respectively in the
0, 1 and 2-inch wastewater treatment areas, over half of which is
located in the upper foot of soil. The same treatments contained,
respectively, 92.8, 74.0 and 79.7 tons of organic matter to a depth
of five feet, approximately 70% of which is located in the upper foot
of soil. The annual nitrogen and organic matter loads from the waste-
water applied to the corn rotation have been relatively small,
averaging about 160 pounds of nitrogen and approximately 500 pounds of
organic matter per acre per year for the 2-inch per week treatment, •
with an average of 50 inches of wastewater being applied annually.
With cognizance of the nitrogen removals in the crops and leaching
losses of nitrate and the small amount of organic matter added in the
effluent it is understandable why one should not expect to find large
changes in total nitrogen or organic matter.^
204
-------
Table 98. Chemical Characteristics of Soil Samples at Five Depths from Plots of the Corn Rotation
Area Receiving Various Levels of Wastewater. 1963
o
en
Depth
inches
0-12
12-24
,
24-36
36-48
48-60
Wastewater Level
inches/week
0
1
2
0
1
2
0
1
2
0
1
2
0
1
2
K+
0.81
0.63
0.63
0.51
0.45
0.53
0.67
0.42
0.44
0.65
0.47
0.61
0.67
0.57
0.60
Exchangeable Cations
Ca2* Mg2"1" Na+ H* E.
M,E./100g
4.95
5.44
4.81
2.83
3.05
3.24
1.71
2.36
1.49
1.74
1.58
0.97
0.99
1.22
0.84
0.27
0.34
0.43
0.46
0.70
1.01
0.85
1.83
1.42
1.01
1.61
1.12
0.88
1.45
1.30
0.09
0.26
0.26
0.09
0.12
0.19
0.09
0.09
0.10
0.10
0.10
0.14
0.09
0.09
0.09
^6.69
6.29
6.24
7.79
6.46
7.23
10.29
9.40
10.20
10.41
8.74
8.57
8.48
8.12
9.37
0
2
2
0
1
1
0
0
0
0
0
1
0
0
0
S.P.I/
%
.8
.1
.1
.8
.1
.6
.7
.6
.7
.7
.8
.2
.8
.8
.7
B.S.I/
1
47.0
51.5
49.6
33.3
40.1
40.6
24.6
33.4
25.3
27.7
30.1
24.9
24.8
28.8
23.3
PH
6.0
6.4
6.2
5.1
5.4
5.2
4.9
5.0
4.9
4.8
4.9
4.8
4.9
4.9
5.0
Mnl/
vg/g
14.62
14.92
13.77
17.97
23.56
14.12
8.48
23.32
15.40
12.68
22.43
18.16
18.37
24.41
17.82
—' Exchangeable sodium percentage.
2/
—' Base saturation.
3/
—' Extracted with exchangeable bases.
-------
Table 99. Chemical Characteristics of Soil Samples at Five Depths from Plots of the Corn Rotation'
Area Receiving Various Levels of Wastewater. 1965
to
o
Depth
inches
0-12
12-24
24-36
36-48
48-60
Wastewater Level
inches/week
0
1
2
0
1
2
0
1
2
0
1
2
0
1
2
K+
0.58
0.47
0.50
0.42
0.43
0.38
0.47
0.47
0.47
0.32
0.39
0.41
0.39
0.33
0.32
Ca2*
M
4.74
4.27
5.06
2.62
2.45
3.42
1.76
1.19
1.56
0.92
0.83
1.21
0.84
0.77
0.93
Exchangeable Cations
Mg2+ Na+ H+ E.S.P.i/
.E./100g %
0.23
0.51
0.76
0.46
0.76
0.84
1.20
1.17
1.01
1.04
1.37
1.26
1.09
1.41
1.13
0.51
0.66
0.66
0.16
0.36
0.56
0.15
0.21
0.26
0.19
0.23
0.29
0.18
0.22
0.27
6.55
6.34 -
6.24
7.19
8.60
8.69
8.96
9.15
8.92
9.93
10.21
9.77
9.88
11.07
10.31
4.0
5.4
4.9
1.5
2.9
4.0
1.2
1.7
2.2
1.5
1.7
2.2
1.5
1.6
2.1
B.
48
48
53
34
31
37
28
24
27
19
21
24
19
20
20
s.i/
.1
.2
.5
.6
.7
.4
.6
.9
.1
.6
.9
.3
.9
.2
.5
pH
6.0
6.2
6.4
5.1
5.1
5.4
5.0
4.9
5.2
4.8
4.8
5.0
4.8
4.8
4.9
Mn-/
yg/g
4.05
3.04
2.78
6.04
6.59
5.70
8.39
8.44
5.46
7.10
8.97
6.50
8.00
11.06
8.28
-' Exchangeable sodium percentage.
21
—' Base saturation.
— Extracted with exchangeable bases.
-------
Table 100. Chemical Characteristics of Soil Samples at Five Depths from Plots of the Corn Rotation
Area Receiving Various Levels of Wastewater. 1966
t-o
o
Depth
inches
0-12
12-24
24-36
36-48
48-60
Wastewater Level
inches/week
0
1
2
0
1
2
0
1
2
0
1
2
0
1
2
K+
0.64
0.72
0.54
0.41
0.36
0.51
0.39
0.35
0.44
0.57
0.43
0.38
0.48
0.51
0.57
Ca2+
M.
6.00
5.50
5.41
3.48
3.15
2.95
1.88
1.63
1.54
1.22
0.66
0.90
0.87
0.69
0.70
Exchangeable Cations
Mg2+ Na+ H+ E.
E./lOOg
0.25
0.90
1.13
0.44
0.51
0.55
0.95
1.03
0.91
1.14
1.05
1.05
1.30
1.22
1.21
0.15
0.46
0.50
0.13
0.30
0.32
0.11
0.19
0.23
0.10
0.16
0.20
0.12
0.16
0.20
14.39
8.30
7.62
10.09
12.90
15.06
9,53
8 48
10.58
10.36
11.03
13.12
12.76
11.87
11.63
0
2
3
0
1
1
0
1
1
0
1
1
0
1
1
S.P.I/
%
.7
.9
.3
.9
.8
.7
.9
.6
.7
.7
.2
.3
.8
.1
.4
B.S.i/
%
33.9
47.7
49.9
30.7
25.1
22.3
25.5
27.4
22.8
22.6
17.4
16.2
17.8
17.9
18.7
PH
6.2
6.4
6.6
5.4
5.5
5.6
5.1
5.0
5.1
4.8
4.8
4.9
4.9
4.8
4.8
Mnl/ '
yg/g
3.75
3.36
2.72
3.46
3.72
3.79
4.68
6.11
6.08
6.08
5.68
6.23
6.48
7.26
7.40
— Exchangeable sodium percentage.
2/
—' Base saturation.
— Extracted with exchangeable bases.
-------
Table 101. Chemical Characteristics of Soil Samples at Five Depths from Plots of the Corn Rotation
Area Receiving Various Levels of Wastewater. 1967
to
o
00
Depth
inches
0-12
12-24
24-36
36-48
48-60
Wastewater Level
inches/week
0
1
2
0
1
2
0
1
2
0
1
2
0
1
2
K+
0.65
0.22
0.37
0.26
0.37
0.40
0.31
0.49
0.47
0.39
0.43
0.33
0.25
0.27
0.37
Ca2+
M
5.15
5.32
5.23
3.12
3.32
2.99
1.81
1.94
1.54
1.11
1.48
1.07
0.96
1.06
0.80
Exchangeable Cations
Mg2"*" Na+ H+ E.S
.E./100g %
0.18
0.43
0.47
0.58
0.77
0.68
0.98
1.36
0.92
1.14
1.46
1.21
0.93
1.26
1.07
0.18
0.43
0.47
0.24
0.43
0.46
0.24
0.33
0.42
0.24
0.33
0.44
0.16
0.19
0.24
7.67
7.95
7.07
9.45
8.48
9.32
8.97
8.85
10.11
9.31
9.25
9.68
9.06
8.55
9.43
1.
2.
3.
1.
3.
3.
2.
2.
3.
2.
2.
3.
1.
1.
2.
pi/
• f •
3
9
3
8
2
3
0
5
1
0
6
5
4
7
0 •
B.S.i/
%
44.5
46.1
50.6
30.8
36.6
32.7
27.1
31.8
24.9
23.6
28.6
24.0
20.2
24.5
20.8
pH
5.9
6.4
6.4
5.5
5.7
5.5
5.2
5.2
5.1
4.9
5.1
5.0
4.9
5.0
5.0
Mr^/
Vg/g
4.22
3.50
2.82
2.75
3.93
4.85
3.37
4.79
6.46
3.42
5.02
5.43
4.04
4.76
4.15
—' Exchangeable sodium percentage.
2 /
— Base saturation.
f-' Extracted with exchangeable bases.
-------
Table 102. Chemical Characteristics of Soil Samples at Five Depths from Plots of the Com Rotation
Area Receiving Various Levels of Wastewater. 1968
O
tO
MMPMMMIMMIMBMB
Depth
inches
0-12
12-24
24-36
36-48
48-60
MMBMMBWMIIIMMMMHHM^IIBVHMHMW-a^BIM
Wastewater Level
inches/week
0
1
2
0
1
2
0
1
2
0
1
2
0
1
2
••^•I^^^BaiaattHi^M
K*
0.50
0.46
0.62
0.59
0.24
0.18
0.36
0.18
0.31
0.57
0.46
0.26
0.34
0.42
0.44
MM^HBOMB^^MMi^H
Ca2+
M.
5.01
5.28
4.88
3.41
3.04
3.44
1.90
1.74
2.12
1.31
1.50
1.64
0.95
1.26
1.17
ltart^BMHWMMH_M^MHMIM^MMMM^^BMBMIf^BWlMBW^MI^«B«^M
Exchangeable Cations*
%2+ Na* H* E.S.P.-^
E./10@g %
0.24
1.00
1.29
0.43
0.70
0.74
0.72
1.15
1.04
0.95
1.40
1.25
0.99
1.63
1.20
0.25
0.47
0.54
0.26
0.39
0.47
0.18
0.29
0.40
0.20
0.30
0.36
0.19
0.31
0.33
9.53
8.91
8.67
10.21
10.79
11.52
13.10
12.05
12.04
12.84
12.38
11.73
11.90
13.38
13.01
1.
2.
3.
1.
2.
2.
1.
1.
2.
1.
1.
2.
1.
1.
2.
6
9
4
7
6
9
1
9
5
3
9
4
3
8
0
••••••^•••••••^••••••B
B.S.2/
1
38.6
44.7
45.8
31.5
28.8
29.5
19.4
21.8
24.3
19.1
22.8
23.0
17.2
21.3
19.4
•^WHMHOMMlM
PH
5.9
6.4
6.5
5.5
5.5
5.7
5.0
5.2
5.3
5.0
5.0
5.1
4.9
4.9
5.0
Mn-/
vg/g
3.61
2.78
2.31
2.45
3.70
2.51
3.03
4.34
3.57
2.12
3.64
4.36
2.30
4.06
4.98
—' Exchangeable sodiun percentage.
2/
—' Base saturation.
—' Extracted with exchangeable bases.
-------
Table 103. Chemical Characteristics of Soil Samples- at Five, Depths from Plots of the Corn Rotation.
Area Receiving Various Levels of Wastewater. 1969
ts>
H»
O
Depth
inches.
0-12
12-24
24-36
36-48
48-60
Wastewater Level
inches/week
0
1
2
0
1
2
0
1
2
0
1
2
0
1
2
K+
0.15
0.42
0.59
0.10
0.18
0.24
0.33
0.09
0.14
0.28
0.18
0.25
0.54
0.40
0.33
Ca2+
M.
4.98'..
5.75
5.65
3.25
4.14
3.64
2.30
2.48
2.09
1.89
1.92
1.34
1.46
1.74
1.02
Exchangeable Cations
Mg2+ Na+ H+ E.S
E./lOOg %
0.26
1.11
1.40
0.34
0.68
0.80
0.74
1.17
1.02
0.89
1.30
1.28
0.99
1.43
1.24
0.21.
0.43.
0.44
0.19
0.42
0.43
0.18
0.29
0.37
0.16
0.28
0.30
0.19
0.20
0.32
10.79
9.92"
9.79
10.69
10.01
10.06
11.54
11.76
11.75
12.46
12.76
13.04
11.18
12.25
11.38
1.
2.
2.
1.
2.
2.
1.
1.
2.
1.
1.
1.
1.
1.
2.
pi/
• A »^^
3
3
5
3
7
8
2
8
4
0
7
8
3
2
2
B.S.I/
%
34.2
43.7
45.2
26.6
35.1
33.7
23.5
25.5
23.6
20.5
22.4
19.6
22.1
23.5
20.4
pH
5.6
6.3
6.3
5.1
5.8
5.6
5.1
5.1
5.2
5.0
5.1
5.1
4.9
5.0
4.9
Mr£/
Ug/g
7.61
4.03
4.35
3.35
2.63
3.97
4.55
5.40
6.75
4.12
5.61
6.20
4.06
7.28
6.67
—' Exchangeable sodium percentage.
2/
—' Base saturation.
—' Extracted with exchangeable bases.
-------
Table 104. Chemical Characteristics of Soil Samples at Five Depths from the Reed Canarygrass Area
Which Received Two Inches of Wastewater Per Week. 1969
Ni
Depth
inches
0-12
12-24
24-36
36-48
48-60
v+ ro2+
K Ca
M.E
0.33 5.72
0.06 3.25
0.34 2.04
0.32 1.63
0.53 1.25
Exchangeable
Mg2+ Na+
• 100/g
1.17 0.48
0.89 0.45
1.27 0.44
1.32 0.27
1.43 0.26
Cations
H+ E
9.91
11.26
12.45
12.22
11.28
SP '
• Jr •
%
2.7
2.8
2.7
1.7
1.8
B.S.2/
%
43.7
29.2
24.7
22.5
23.5
N
%
0.133
0.048
0.032
0.022
0.021
O.M.
*
3.01
0.82
0.34
0.18
0.09
Mn3/
4.72
12.60
9.49
7.99
5.26
B3/
ug/g
0.63
0.26
0.19
0.29
0.63
Cl
59.4
49.7
57.7
53.5
56.5
pH
6.4
5.7
5.4
5.2
5.0
—' Exchangeable-sodium percentage.
?/
— Base saturation.
— Extracted with exchangeable bases.
-------
Table 105. Chemical Characteristics of Soil Samples at Five Depths from Plots of the Hardwood
Area on Morrison Sandy Loam Soil at the Gamelands Which Received 0 and 2 Inches of
Wastewater Weekly. 1967
Exchangeable Cations
Soil
Depth
inches
0-12
12-24
24-36
36-48
48-60
Wastewater
Level
inches/week
0
2
0
2
0
2
0
2
0
2
K+
0.08
0.15
0.24
0.24
0.25
0.25
0.43
0.46
0.33
0.44
Ca2+
M.
0.34
0.91
0.36
0.50
0.45
0.86
0.34
1.19
0.30
1.20
Mg2+ Na+
E./lOOg
0.00 0.16
0.18 0.27
0.00 0.16
0.09 0.21
0.09 0.19
0.35 0.26
0.07 0.16
0.63 0.24
0.05 0.18
0.63 0.24
H+
5.20
4.15
3.75
1.85
3.45
2.65
2.75
2.75
1.65
3.80
E.S.P.i/
%
2.8
4.8
3.5
7.3
4.3
5.9
4.3
4.6
7.2
3.8
B.S.2/
*
10.0
26.7
16.8
36.0
22.1
39.4
26.7
47.8
34.3
39.8
Mnl/
12,6
6.8
7.8
4.6
4.4
6.2
5.1
4.4
4.6
4.7
T&
vg/g
0.40
0.45
0.60
0.55
0.10
0.15
0.35
0.45
0.35
0.45
Cl
43.3
40.4
43.3
48.7
32.4
37.8
24.6
21.7
29.7
29.4
pH
4.9
5.5
5.0
5.3
5.4
5.5
5.4
5.9
5.4
5.7
—' Exchangeable sodium percentage.
—' Base saturation.
— Extracted with exchangeable bases.
-------
Table 106. Chloride Content of Soil Samples at Five Depths from Plots
of the Com Rotation Area Receiving Various Levels of
Wastewater.
Wastewater ,-, ., I/ .
Depth Level Chloride-/ -micrograms
inches inches/week 1963 1965 1966 1967
0-12
12-24
24-36
36-48
48-60
0
1
2
0
1
2
0
1
2
0
1
2
0
1
2
20.3
27.4
27.9
16.6
36.6
38.1
27.2
40.6
45.7
41.5
33.0
65.7
26.8
29.2
42.0
7.7
24.6
16.6
12.8
19.9
15.6
12.5
49.5
36.1
12.5
32.1
37.8
23.6
31.5
36.4
31.1
35.2
37.6
25.8
31.4
33.8
44.7
59.0
58.6
33.3
63.8
70.6
26.2
47.8
61.5
29.9
40.2
53.4
27.7
37.6
41.1
37.1
41.3
39.0
46.5
60.9
69.0
53.8
59.9
66.2
per gram
1968 1969
36.0
40.6
37.2
29.4
37.6
43.5
38.1
44.1
39.6
38.5
43.9
62.0
31.6
56.2
61.6
44.1
41.2
46.6
44.1
45.7
48.4
47.3
50.0
58.8
40.4
55.2
69.7
49.4
67.1
80.2
— Extracted with 0.05 Normal ammonium nitrate.
213
-------
Table 107. Boron Content of Soil Samples at Five Depths from Plots
of the Com Rotation Area Receiving Various Levels of
Wastewater.
Depth
inches
0-12
12-24
24-36
36-48
48-60
Wastewater
Level
inches/week
0
1
2
0
1
2
0
1
2
0
1
2
0
1
2
Boron— -micrograms
1963 1965 1967
0.75
0.68
1.07
0.53
0.57
0.56
0.42
0.39
0.38
1.68
1.41
0.87
1.76
1.73
1.55
1.03
1.23
0.80
1.10
1.23
1.36
1.31
1.16
1.15
0.92
1.13
1.22
0.75
0.80
0.96
0.63
0.50
0.84
0.50
0.61
0.80
0.24
0.50
0.72
0.35
0.38
0.64
0.37
0.24
0.47
per gram
1968 1969
0.48
0.71
0.83
0.70
0.28
0.49
0.36
0.36
0.45
0.38
0.15
0.32
0.38
0.60
0.54
0.12
0.61
0.80
0.08
0.22
0.32
0.22
0.24
0.13
0.24
0.14
0.32
0.64
0.34
0.48
— Boron extracted during extraction of exchangeable bases.
214
-------
Table 108. Nitrogen and Organic Matter Content of Soil Sanples at
Five Depths from Plots of the Corn Rotation Area Receiving
Various Levels of Wastewater.
Nitrogen - 1
Wastewater v
Depth Level Year
inches inches/week 1963 1965 1966
0-12
12-24
24-36
36-48
48-60
0
1
2
0
1
2
0
1
2
0
1
2
0
1
2
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
113
131
094
050
038
037
024
024
025
016
016
015
016
014
014
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
090
090
091
026
027
032
020
015
015
016
014
018
013
015
014
0.121
0.130
0.137
0.058
0.063
0.069
0.031
0.024
0.032
0.026
0.020
0.025
0.019
0.012
0.015
1968
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
109
108
106
038
032
032
025
022
018
018
021
021
013
013
017
Organic Matter - 1
Year
1963 1965 1968
2.75
2.51
2.41
0.42
0.42
0.32
0.21
0.20
0.17
0.22
0.14
0.14
0.13
0.09
0.11
2.52
2.10
2.06
0.52
0.57
0.67
0.16
0.13
0.19
0.12
0.13
0.12
0.11
0.14
0.16
3.08
2.60
2.84
0.91
0.36
0.58
0.44
0.33
0.21
0.15
0.24
0.18
0.11
0.17
0.15
215
-------
Soil Phosphorus Relationships
Previous Work. The removal of phosphorus by soil from a solution in
contact with it is widely believed to be due to adsorption. This
conclusion is supported by the fact that various investigators have
found that the pattern of removal of phosphorus from solution closely
agreed with the Langmuir adsorption isotherm (58, 59, 60).
The Langmuir (61) equation was originally applied to the adsorption
of gases on plane surfaces but has since been used successfully to
explain the pattern of adsorption of many substances from solution.
The Langmuir equation,
x _ Kbc m
may be written in its linear form,
^_ - i- + £ (2)
x/m Kb b
where
c = equilibrium concentration,
x/m = amount of adsorbate per unit weight of adsorbent
K = constant relating the bonding energy of the adsorbent
for the adsorbate,
b = adsorption maximum or the amount adsorbed when all
sites are occupied
Langmuir in the development of this equation had made certain assump-
tions: firstly, that there were on the surface of the adsorbent,
discrete points at which adsorption could occur and, secondly, that
each of these points could independently hold only one adsorbed
molecule. He suggested that any anomalous behavior might be due to
(1) porous bodies that would cause internal adsorption; (2) condensa-
tion, if the vapor was saturated; and (3) solution or absorption being
mistaken for adsorption.
*
A number of workers have also found conformity of phosphorus adsorption
with the Freundlich adsorption isotherm (62, 63, 64).
The Freundlich adsorption equation relates the amount of adsorbate to
the final concentration of the solution from which adsorption occurs.
It is
- = KC1/n (3)
m
216
-------
or written in linear form is
log * = log K + I log C
m n
where
x/m = amount of adsorbate per unit weight of adsorbent
C = equilibrium concentration
K and n are constants
According to the Freundlich equation, the amount adsorbed increases
indefinitely with increasing concentration or pressure. A linear plot
of the logarithmic form of the equation is called a Freundlich adsorp-
tion isotherm.
The Freundlich equation is an empirical one, having been deduced from
thermodynamic considerations, using empirical methods for determining
the change in surface tension with changes in concentration. It,
therefore, does not give any insight into the mechanism of adsorption
nor is it satisfactory for high coverages. However, it is sometimes
more successful than the Langmuir equation from the empirical stand-
point. The Langmuir equation furthermore is not a satisfactory
representation of physical-adsorption data. It has been found for
example that at apparent saturation of the surface, only a small
percentage of the total area is covered (65). This deviation would
result from a heterogeneous surface, that is, a surface on which
different regions have different affinities for the substances being
adsorbed.
In comparing both equations for use in the adsorption of phosphorus
by soils, Olsen and Watanabe (60) stated that the Langmuir equation
was more applicable to relatively small amounts of adsorbed phosphorus
'and thus at lower equilibrium concentrations. The Freundlich equation,
on the other hand, was applicable to a wide range of equilibrium
concentrations. The Langmuir equation, unlike that of Freundlich,
enabled one to calculate the adsorption maximum which was found to be
closely correlated with surface area. In addition, Olsen and Watanabe
(60) and Hsu and Rennie (66) obtained results that indicated that both
adsorption isotherms were followed. It was noted, however (60), that
the adsorption pattern agreed more closely with the Langmuir adsorp-
tion isotherm. -
Various equilibration periods have been used. Russel and Low (64)
employed a period of one hour while Hsu (59), Rennie and McKercher
(67) and Weir and Soper (68) used an equilibration period of six hours.
Other investigators (60) have reported an equilibration period of 24
hours but Seatz (69) used seven days and that in the study by Davis
(62) was 16 days. The latter author found a slow attainment of
217
-------
equilibrium even after this time and suggested that other processes
besides adsorption were occurring since the equilibrium resulting
from adsorption is supposed to be a rapid one.
A change in the slope of the adsorption isotherm plotted by Olsen
and Watanabe (60) occurred at equilibrium concentrations in the range
4-7 x ID'4 moles/£(12-22 mg/£). Similar observations were made by
Rennie and McKercher (67) at a final concentration of 20 mg/£, and by
Weir and Soper (68) at around 30 mg/£. The isotherms plotted above
these concentrations were all lower in slope than the isotherms plot-
ted at the lower concentrations and adsorption maxima calculated
from them were considerably higher than those given for the initial
adsorption reaction. It is suggested (68) that this secondary re-
action could be either a true adsorption or precipitation. Oft the
other hand, it was thought (67) that this anomaly indicated that
either new centers of adsorption had been found or multi-molecular
adsorption had occurred.
Although the adherence of phosphorus adsorption to the Langmuir and
Freundlich isotherms probably indicates adsorption of a monomolecular
layer, it does not necessarily imply an adsorption reaction. Hsu (59)
maintains that the application of the Langmuir adsorption isotherm to
phosphorus fixation is subject to certain limitations namely, pH of
the solution, absence of exchangeable aluminum and the equilibration
period. When phosphorus solution at pH 7 was shaken for a relatively
short period (6 hours) with slightly acid soil in the absence of
exchangeable aluminum then adsorption occurred and the Langmuir ad-
sorption isotherm was followed. Fixation, he pointed out, would be
very slow unless the reaction was carried out in a strongly acidic
medium or if exchangeable aluminum was present.
Davis (62) also stated that adherence to the Freundlich adsorption
isotherm did not necessarily imply that fixation was due to adsorption.
The slow rate of reversal of fixation made adsorption doubtful as a
fixation process.
The fixation of phosphorus has been found to be inversely related to
the amount of organic matter present in the soil (70, 71). Expressed
differently, the addition of organic matter to the soil significantly
reduced the fixation of phosphorus and simultaneously increased its
availability. Doughty (71) also found that although a soil naturally
low in organic matter had a high phosphorus fixing capacity, the
oxidation of organic matter with hydrogen peroxide caused a decrease
in the fixation of phosphorus. Loss of fixing power was attributed
to the saturation of the fixing material with the phosphate liberated
from the organic matter during oxidation.
Swenson et al. (72) stated that organic matter prevented phosphorus
from combining with iron and aluminum and caused the release of
218
-------
combined phosphorus by the formation of stable iron and aluminum com-
plexes with the organic acids produced by decomposition of the organic
matter.
Phosphorus Adsorption Studies. In May, 1965 soil samples were obtain-
ed! from the com rotation control area for use in a phosphorus adsorp-
tion study (g). The samples were taken randomly from the 240 x 800
foot area using a manually operated soil augur. The material from
one-foot intervals to a depth of five feet was composited to give bulk
samples, one for each depth interval. Some physical and chemical
characteristics of these samples is shown in Table 109. These same
materials were also used in ABS and cation adsorption studies.
Five gram samples of <2.0mm sieve size were shaken for 24 hours with
50 ml of KH2P04 solutions containing 15, 30, 40, 60, 100, 125, 150 and
200 mg P per liter. After centrifuging, the supernatant solution was
analyzed for P using the sulfuric-molybdate procedure in Jackson (73,
pg 141). The same adsorption procedure was used with the same soil
which had been treated with hydrogen peroxide to remove organic matter.
The oxidized sample was washed three times by centrifugation and de-
cantation with distilled water and then air dried before being used
in the adsorption studies.
Adsorption data for untreated and treated (H202 oxidized) soil from
the five depths are shown in Tables 110 and 111. The data plotted
according to the Langmuir adsorption equation are shown in Figures 58
through 62.
At each depth the data appeared to conform to two adsorption isotherms,
the one at the higher concentrations being less steep in slope. For
untreated and treated soil from the 1-foot zone, which had the highest
organic matter content, the break in slope occurred at an equilibrium
concentration of 15.5 mg P per liter (0.5 millimoles P per liter).
For samples deeper in the profile the break in slope occurred at
lower equilibrium concentrations, ranging down to about 6.5 mg P per
liter (0.2 millimoles P per liter).
Other workers have also reported the presence of bi-modal adsorption
isotherms. Olsen and Watanabe (60) found that for different soils the
first isotherm terminated at concentrations ranging from 12 to 25 mg P
per liter. Weir and Soper (68) also reported initial adherence to the
Langmuir isotherm only at final concentrations below 25-30 mg P per
liter.
Adsorption maxima computed from the initial isotherms were smaller
than those computed from the second isotherm. Since the initial iso-
therm is believed to represent the reversible, instantaneous surface
reaction defined by the Langmuir concept, only the adsorption maximum
computed from this isotherm can be mathematically justified. The
219
-------
ts>
ts>
Table 109. Physical and Chemical Characteristics of Soil Samples from Control Plots of the Com
Rotation Area (8)
Depth
(inches)
0-12
12-24
24-36
36-48
48-60
Sand
33.0
28.3
28.0
27.8
29.3
Silt
C Qt *\
I V J
34.4
31.7
23.9
23.6
20.7
Clay
C*)
32.6
40.0
48.1
48.6
50.0
Organic
Matter
(I)
3.34
0.93
0.48
0.25
0.19
pH
5.6
4.7
4.6
4.5
4.5
Acid- Soli
P
(ppm)
3.50
1.75
1.75
1.50
1.50
I Exchangeable
H+
6.95
8.66
6.95
10.22
7.80
Ca2+
5.60
3.40
2.60
1.80
1.60
Cations (me/ lOOg)
... 2+
Mg
0.42
0.73
1.33
1.25
1.25
K+
0.18
0.18
0.21
0.21
0.22
Na*
0.25
0.20
0.17
0.19
0.22
Dilute Bray, 0.03N-NH4F in 0.025 N-HC1, extractable.
-------
N)
Table 110. Equilibrium Concentration (mmole/A) and Phosphorus Adsorbed (mg/g) by Untreated
from Various Depths (8)
0-12
Eq Cone
0.0363
0.1581
0.3097
0.5065
0.7677
1.6645
2.1806
3.0742
4.4194
P Ads
0.1478
0.2571
0.3141
0.3231
0.3821
0.4741
0.5791
0.5071
0.5501
Depth of Sampling, Inches
12-24 24-36 36-48
Eq Cone
0.0114
0.0452
0.1065
0.1952
0.7806
1.3452
1.8065
2.9839
4.5484
P Ms
0.3025
0.3960
0.4470
0.5595
0.7480
0.8380
0.9000
0.9950
1.1000
Eq Cone
0.0323
0.0645
0.1581
0.6387
1.1387
1.6774
2.8871
4.2581
—
P Ads
0.4000
0.4600
0.5710
0.7920
0.9020
0.9400
1.02501
1.1900
—
Eq Cone
0.0123
0.0452
0.1129
0.1855
0.6387
1.3194
1.6774
2.8387
4.3871
P Ads
0.3022
0.3960
0.4450
0.5625
0.7920
0.8460
0.9400
1.0400
1.1500
48-60
Eq Cone
0.0131
0.0452
0.1161
0.2371
0.7419
1.3581
1.7258
2.8871
4.5161
P Ads
0.3019
0.3960
0.4440
0.5465
0.7600
0.8340
0.9250
1.0250
1.1100
— Not treated with hydrogen peroxide.
-------
to
to
IsJ
Table 111. Equilibrium Concentration (mmole/Jl) and Phosphorus Adsorbed (mg/g) by Treated Soil—
from Various Depths (8)
Depth of Sampling, Inches
0-12
Eq Cone
0.0645
0.2161
0.4194
0.5484
1.6452
2.9839
P Ads
0.1263
0.2330
0.2800
0.3240
0.4900
0.5750
12-24
Eq Cone
0.0266
0.1032
0.2194
1.1742
2,4032
3.8064
P Ads
0.2917
0.3780
0.4260
0.6360
0.7550
0.8600
24-36
Eq Cone
0.0161
0.0839
0.1548
0.9290
2.0968
3.3871
P Ads
0.2950
0.3840
0.4460
0.7320
0.8500
0.9900
36-48
Eq Cone
0.0160
0.0645
0.1935
0.9806
2.1613
3.5484
P Ads
0.2950
0.3900
0.4340
0.6960
0.8300
0.9400
48-60
Eq Cone
0.0155
0.0516
0.1935
1.0000
2.2097
3.5000
P Ads
0.2950
0.3840
0.4340
0.6900
0.8150
0.9550
— Treated with hydrogen peroxide to remove organic matter.
-------
O
•P
o
I-l
X
•o
flj
00
o
§
u
a*
w
0
Untreated soil
X X Treated soil
2 3
Eq. cone. (millimoles/£)
to
0)
•H
8
S
oo
I v-•'
CM
O C
-------
en
"3
o
g
o
•
w
o o Untreated soil
X x Treated soil
2 3
Eq. cone. (millimoles/£)
o
a
*\
to
cvr
(M
"0
R
rt
00
rrf
•B b
Co *rj
C
4$
&s
en
tn
224
-------
70 r-
Untreated soil
X X Treated soil
2 3
Eq. cone. (millimoles/£)
225
-------
Q
iH
X
CO
•a
cfl
O
O
cr
w
70 r-
60 h
50 h
401-
Untreated soil
X X Treated soil
l
2 3
Eq. cone. (millimoles/A)
a
•M
CO
rj-
I
VO
to
226
-------
70 r-
-3-
I
CO
"8
u
g
u
T)
CD
•P
o
-------
second isotherm is believed to be associated with a slower, continuing,
less-reversible reaction with oxy- and hydroxy compounds of iron and
aluminum. The adsorption maxima computed from the initial isotherm
are shown in Table 112 for both the untreated and oxidized soil. In
untreated soil the adsorption maximum increased from 350 yg P/gram of
soil for the upper foot to 570 yg P/g at three feet then decreased
sharply to 350 yg P/g in the fifth foot. Removal of organic matter by
oxidation resulted in relatively small changes, both positive and nega-
tive, in adsorption maxima except in the fifth foot where the increase
was approximately 341 and in the second foot where the decrease was
221. The soil properties in Table 109 offer no consistent explanation
of the pattern of adsorption maxima. Organic matter decreased sharply
with depth into the second foot and then more slowly, while clay con-
tent increased sharply from the first foot into the second foot and
third foot and then remained almost constant. Oxidation of organic
matter may have released iron and aluminum and resulted in increased
adsorption capacity but phosphorus released from the organic matter
could also have reacted with some of the adsorption sites and hence
decreased adsorption capacity. The consequences of heating and wash-
ing the soils during the oxidation procedure may have been positive
or negative.
Table 112. Phosphorus Langmuir Adsorption Maxima (yg/g) of Untreated
and Treated Soil in Relation to Depth (8)
Depth
(in.)
0-12
12-24
24-36
36-48
48-60
Adsorption Maxima
Untreated
350
540
570
450
350
(wg/g)1
fj
Treated"4
390
420
530
460
470
Calculated from lower portion of Langmuir curve
2
Treated with hydrogen peroxide to remove organic matter
When the adsorption data were plotted according to the Freundlich
adsorption equation as shown in Figures 63 through 67 the patterns of
adsorption seemed to be more logically relatable to clay content,
particularly if one looks at the adsorption value at an equilibrium
concentration of 100 mg P/l. The values in Table 113 relate positively
to clay content and negatively with respect to organic matter content
in the untreated soil and the soil with the greatest amount of organic
228
-------
0.8
to
TJ
41
•8
o
9
•O
CO
P<
60 80
Eq. cone. (mg/£)
100
120
140
Figuye 63, Phosphorus Adsorption Data for H202-Treated and Uhtreated Soil, 0-12 Indies, Plotted
According to the Freundlich Equation (8).
-------
IS)
w
CD
?
•o
-------
1.2r-
N)
00
00
3
T3
-------
00
O
tn
a 0.6
0
20
40
o Untreated soil
X X Treated soil
60 80
Eq. cone. (mg/£)
100
120
140
Figure 66. Phosphorus Adsorption Data for H202-Treated and Untreated Soil, 36-48 inches, Plotted
According to the Freundlich Equation (8).
-------
1.1
ts>
CaO
0)
,0
M
O
10
O.
0.3
0.2
0
20
40
Untreated soil
X X Treated soil
60 80
Eq. cone. (mg/£)
100
120
140
Figure 67. Phosphorus Adsorption Data for F^C^-Treated and Untreated Soil, 48-60 inches, Plotted
According to the Freundlich Equation (8).
-------
Table 113. Phosphorus Adsorbed at an Equilibrium Concentration of
100 mg P/l as Determined from the Freundlich Adsorption
Isotherms.
Phosphorus adsorbed - yg/g soil
Soil Depth /
feet IMtreated Treated*
1 510
2 990
3 1070
4 1060
5 1030
590
810
970
920
920
—' Oxidized with H,09 to remove organic matter.
-------
.Table 114. Bray Phosphorus (yg/g) in Soil Samples Obtained in Different Years at Five Depths
from Plots Receiving Various Levels of Wastewater Applications.
01
in
Plot Location
and
Soil Type
Corn Rotation -
Hublersburg
clay loam
•
Soil
Depth
inches
0-12
12-24
24-36
36-48
48-60
1963
1965
Wastewater -
0
18.80
3.15
1.35
1.25
1.25
1
14.90
2.05
1.40
0.90
1.10
1967
2
18.50
1.00
1.10
1.10
1.32
0
21.60
1.80
1.35
1.35
0.45
1
25.15
' 3.20
1.20
0.70
0.20
1968
Wastewater -
Game land -
Hardwood
Morrison
sandy loam
»
0-12
12-24
24-36
36-48
48-60
0
28.50
1.90
2.20
2.35
0.75
1
25.50
1.90
0.65
1.25
1.20
1967
2
41.65
0.95
0.80
0.75
1.35
0
33.30
4.70
2.65
1.40
1.35
1
31.60
2.50
1.60
2.20
1.25
inches
2
32.10
2.35
1.10
0.70
0.10
inches
2
60.35
6.40
2.65
1.10
0.85
1966
per week
0
19.75
2.20
1.50
1.45
0.90
1
26.85
1.80
1.90
1.20
1.15
1969
2
36.95
4.25
1.15
0.90
1.05
per week
0
21.75
4.40
3.75
1.40
1.35
1
32.40
3.15
0.90
1.20
2.25
2
50.65
2.90
1.35
1.05
2.35
i/
2—
29.80
2.70
3.40
0.65
1.05
Wastewater - inches/week
0-12
12-24
24-36
36-48
48-60
0
39.15
7.75
3.75
3.35
2.80
2
61.65
11.10
3.50
2.40
1.45
— Reed canarygrass area - Hublersburg clay loam
-------
substantially since 1963. The increase in the 1-inch per week area
has been only half as great. The control (0-inch per week) area
which has received phosphorus each year through additions of commer-
cial fertilizer has shown only a slight increase over the six years.
Going into the second foot and deeper the differences are small and
erratic indicating that even though phosphorus is getting into the
second foot of soil it has not yet accumulated sufficiently to be
detected by the Bray test.
Even in the 2-inch per week reed canarygrass area which has received
more than twice as much phosphorus as the 2-inch corn rotation area,
an increase in Bray phosphorus in the second foot was not detectable.
In sharp contrast to these two sites on the fine textured Hublersburg
soil, the Bray phosphorus in the second foot of the sandy MDrrison
soil was substantially greater than in the control but in the next
three feet there was no detectable difference in the Bray phosphorus.
So even on this site with a sandy loam soil an average annual appli-
cation of 104 inches of wastewater, which began in Nov, 1965, has not
resulted in a detectable change in available phosphorus in the third
foot. It should also be pointed out that on this site no phosphorus
was being removed in a harvested crop and hence had to recycle through
the soil.
236
-------
Boron Relationships
Previous Work. Because of the potential hazard to vegetation from
boron concentrations above 1 mg/1 and the potential health hazard to
humans of protracted intake of boron at higher concentrations the
U.S. Public Health Service has recommended a limit of 1 mg/1 for
drinking water. In the light of this criteria a more detailed study
of the boron relationships was undertaken by Jardine (55). His
review of the literature indicates that boron toxicity conditions
have been observed with sensitive and semi-tolerant crops in irri-
gated areas of the semi-arid and arid western regions of the United
States when irrigation waters contained as little as 0.5 parts per
million (ppm) of boron in the irrigation water, particularly if
conditions were such that evaporational concentration occurred in the
root zone. In one instance in California (75), prolonged use of
water with 0.4 ppm boron injured the foliage of lemon trees. The
effects of boron were less severe in areas where annual rainfall
exceeded 10 inches.
In humid regions boron deficiency is more prevalent than boron toxi-
city, particularly in the sandy soils which are low in organic matter.
In the Eastern U.S. fertilizers are specifically formulated with as
much as 1% borax for high boron demanding crops such as alfalfa, red
beets, cabbage and cauliflower.
The chemistry of boron in soils is complex (75). Much of the boron
available to growing crops is associated with the organic matter in
the soil (76, 77). Boiling water extractable boron has been highly
correlated with available boron and is commonly used as an estimate
of the need for adding boron to satisfy the nutritional needs of a
growing crop (78). When water soluble boron is added to soils much
of it becomes adsorbed. Biggar and Fireman (79) showed that soils
not only vary in their capacity to fix boron but also in the energy
.with which they retain it. They found that the Langmuir adsorption
equation described the adsorption of boron up to concentrations ranging
from six to 26 milligrams of boron per liter with various soils. The
fixation of boron by soils has been found to be highly pH dependent
over the range from pH 5.5 to pH 9.0, with solubility decreasing as
pH increased. Hatcher et al. (57) attributed increases in amounts of
boron adsorbed after liming acid soils to the exchangeable aluminum
that precipitates as A1(OH)3 at the higher pH. They found that for a
wide variety of soils having pH values in the range 6.3 to 8.3 the
amount of boron adsorbed from a 10 ppm boron solution was highly
correlated with the product of the surface area of the soil and its
citrate-extractable aluminum. Sims and Bingham (80) found that hydroxy
aluminum compounds adsorbed ten times as much boron as hydroxy iron
compounds.
237
-------
The boron study in the Penn State Waste Water Project involved three
phases: 1. A field study of the growth of a boron sensitive crop,
snap beans, on the 0, 1 and 2-inch per week wastewater treatment sec-
tions of the corn rotation area; 2. A greenhouse study to evaluate
the influence of previous wastewater treatment of a soil on the
response of a boron sensitive crop, snap beans; and 3. An adsorption
study to determine the effect of previous wastewater treatment on the
boron fixing power of soil from three depths and the relation of
dithionate-citrate extractable iron to this fixing power.
Field Experiment. In the field experiment, Tekoa 'green snap beans
(Phaseolis vulgaris L.) were planted June 15, 1967 in four rows spaced
three feet apart and 52 feet long in a mid-slope position on the 0, 1
and 2-inch wastewater plots. On Aug 28 plants were harvested from
four 20-foot strips of rows from the two center rows and 'the total
green weight determined. A subsample consisting of several plants from
each 20-foot row sample was weighed green then separated into pods,
leaves and stems and weighed green. The separate parts were then dried
at 145°F, weighed, and ground in a Wiley mill.
A one gram sample of the dried, ground plant tissue was ashed at 485°C
for eight hours then dissolved in a lithium chloride-HCl buffer solu-
tion and analyzed for P, K, Ca, Mg, Mn, Fe, Cu, B, Al, Zn and Na on an
arc emission spectrograph (81). The yields of total bean plants is
shown in Table 115. Yields of the separate parts were in the same
order as the total plant. The data indicate that although the smallest
yield was in the 2-inch treatment area it was not significantly smaller
than in the control area (0-inch). The smaller yield was ascribed to
more severe slug damage which occurred in the wetter plot.
The boron content of the plant parts and the weighted content in the
whole plant are also shown in Table 115. Significantly greater (P =
0.01) boron content was found in the leaves as wastewater application
increased. Boron content of the stems was not significantly different
and only with the 2-inch treatment was boron content of the beans
significantly greater than in the control. On a weighted total plant
basis the boron content of the 1-inch treatment was not significantly
greater than the control but boron content of the whole plant on the
2-inch treatment area was significantly greater (P = 0.01) than in the
0 or 1-inch treatment. The boron contents are not abnormally high and
there was no evidence of boron toxicity on the foliage in the field.
The precipitation during the growth period was below normal in June but
above normal in both July and August and hence not conducive to concen-
trating boron in the soil. Average concentration of boron in the
applied wastewater in 1967 was 0.41 mg/1. During the irrigation period,
April 19 - Oct 25, 1967 the soil water samples obtained with the suction
lysimeters were as shown in Table 116. That boron is washed out is
shown by the suction lysimeter values in Table 116 after irrigation
238
-------
Table 115. Mean Yield and Boron Content of Beans Grown in Field Plots
Receiving Various Levels of Wastewater. 1967 (55)
Wastewater Level - inches per week
012
Fresh weight
Dry weight
Yield - Ib
18.3abV
2.52ab
per 20 -foot row
21. 9b
3.14b
14. 4a
1.98a
Boron content - yg/g
Leaves
Beans
Stems
Whole plant
16.75a
20.25a
14.75a
18.08a
20.25b
22.50ab
14.75a
20.36a
25.50c
25.50b
18.75a
24.22b
— Values in the same row without a common letter are significantly
different at P = 0.01 using Duncan's multiple range test.
Table 116. Average Concentration of Boron (mg/1) in Lysimeter Samples
During Irrigation (adsorption) and Non-irrigation (desorp-
tion) Periods, 1967-1968
Lysimeter
Depth
inches
6
24
48
Wastewater Treatment Area -
0 1
A~
0.06
0.04
0.03
B-
0,03
0.02
0.0.3
A
0.25
0.10
0.07
B
0.10
0.05
0.04
- in./wk.
i*
i
A
0.34
0.20
0.13
>
ri
B
0.12
0.11
0.09
- Irrigation period - 4/19/67 - 10/25/67
-/ Non-irrigation period - 10/26/67 - 4/18/68
ceased in the period Oct 26, 1967 - April 18, 1968. Boron concentration
during the desorption period was decreased 50 to 60%. In regions where
precipitation exceeds potential evapotranspiration it is probable that
at present levels of boron in treated municipal wastewater it is un-
likely that boron would become a health hazard in drinking water or a
239
-------
phytotoxic hazard to any, except the most boron sensitive, crop.
However, since some segments of the detergent industry have been en-
couraging the use of borax as a laundry aid and this might result in
larger inputs of boron in municipal wastewaters a greenhouse experi-
ment was carried out to determine what level of boron in an applied
solution might result in phyto-toxicity over a short haul period.
Greenhouse Experiment. Bulk soil samples were obtained from the three
wastewater treatment plots from successive one foot zones to a depth
of three feet. The samples were air dried and crushed to pass a sieve
with one-fourth inch openings. Ten pounds of soil was weighed into
each of 120 one gallon plastic pots with holes in the bottom for
drainage. The pots were arranged in a greenhouse bench in a triple
lattice design, including a buffer row of six pots at each end of the
triple lattice arrangement. The experiment included 36 treatments in
triplicate, involving a factorial of four boron treatments with nine
different soil materials. The latter included soil from three depths
in three wastewater treatment areas. The boron treatments involved
solutions containing 0.0, 0.5, 5.0 and 10.0 milligrams of boron per
liter.
Nitrogen, phosphorus, potassium, calcium and magnesium were added as
soluble salts in solution to provide the equivalent of 100#(pounds) N,
65# P, 83# K, 142# Ca and 70# Mg per two million pounds of soil.
Boron solutions were added in one inch increments (590 ml per pot).
Each one inch application was equivalent to 0.00, 0.13, 1.30 or 2.60
pounds of boron per two million pounds of soil.
The test plant was the Tekoa green snap bean which had been used in
the field experiment. Two seeds were planted in each pot and later
thinned to one plant per pot. Weekly observations were made on plant
height, leaf color, leaf distortions and other symptoms.
After five applications of the boron solutions at approximately weekly
intervals, differences in boron toxicity had become strongly expressed
and boron irrigations were stopped. Beginning on April 2, six weeks
after planting, irrigation was with distilled water* The plants were
harvested in the ninth week. All leaves which had fallen from the
plant prematurely were saved and weighed with the green plants, then
oven-dried, weighed again and ground in a Wiley mill. Che gram samples
or the total sample, if less than one gram, were ashed and handled for
chemical analyses as were the field experiment samples.
,'
Soil samples (150 to 200 grams) were taken from each pot to full depth
of the pot using a soil sampling tube. Moist subsamples were used for
measuring pH and for extraction of water-soluble manganese (1:10 soil:
water ratio by weight). An air-dried subsample was used for determin-
ation of autoclave-extractable boron which has been found by Lobnik
240
-------
and Baker (Unpublished research at Penn State) to give results not
significantly different from the hot-water extraction method. In the
autoclave procedure 10 grams of dry soil is placed in a 100 ml heat
resistant plastic bottle. Twenty milliliters of distilled water and
0.5 ml of 100% barium chloride solution are added. After covering the
bottles with aluminum foil they are autoclaved for 40 minutes at 21
pounds per square inch steam pressure (110°C). Pressure is reduced
during the last five minutes of autoclaving. After removing from the
autoclave and cooling slightly the supernatant liquid is poured off
into a centrifuge tube and clarified by centrifugation. A two ml
aliquot of the clear supernatant is pipetted into a polypropylene
test tube and boron determined by the Carmine Red procedure (82).
The first observation of stress occurring in the bean plants was in the
fourth week after planting. Some of the plants growing in soil from
the second and third foot began to show interveinal chlorosis. Since
this was not a typical boron toxicity symptom and was not related to
the boron treatments it was finally diagnosed as a manganese toxicity.
The data in Tables 117 through 119 corroborated this diagnosis by the
high concentration of Mn in plants which showed the interveinal
chlorosis.
The severe boron toxicity symptoms of marginal necrosis and yellowing
of the older leaves and cupping downward of all of the leaves occurred
with all soil sources with the 10 mg B treatment. The same symptoms
occurred with the 5.0 mg B treatment but to a lesser degree. None of
the 0.0 or the 0.5 mg B treatments showed boron toxicity symptoms but
did show manganese toxicity symptoms in soils from the second and
third foots.
Because of the interaction of the manganese and boron toxicities the
effect of boron treatment on yield (Table 120) was significant only
with the upper foot of soil in which manganese toxicity did not occur.
Only the 5.0 and 10.0 mg B per liter treatments had significantly
poorer growth than the 0.0 boron treatment. The field wastewater
treatment area from which the soil materials were derived was only
erratically related to the boron treatment effect.
Water soluble Mn was strongly inversely related to pH of the soil
(Table 121) and directly related to Mh content of the plants.
Boron content of the plants, Table 122, was significantly increased
(P • 0.01) by boron treatment particularly with soil from the 2nd and
3rd foots. Previous wastewater treatment which increased the auto-
clave extractable boron in the upper foot of the soil (Table 123) did
not have a significant effect on boron content of the plants. Depth
from which the soil was taken also did not have a significant effect
on boron content of the plant even though the autoclave extractable
boron content of the first foot was significantly greater (P - 0.01)
than both the 2nd and 3rd foot (Table 123).
241
-------
Table 117. Average Plant Weights and Chemical Composition of Bean Plants from Greenhouse Experi-
ment- -Control Area Soil (55)
ISJ
-P*
tsi
Soil*
material
0 - 1'
0-2'
2 - 3'
Boron
treatment
conc'n
mg/1
0.0
0.5
5.0
10.0
0.0
0.5
5.0
10.0
0.0
0.5
5.0
10.0
Plant
weight
grams
6.01
5.60
4.71
3.21
2.03
2.93
1.61
1.37
1.50
1.69
1.41
0.85
Plant tissue content
\
P
0.23
0.21
0.21
0.18
0.11
0.12
0.11
0.13
0.11
0.15
0.13
0.13
Ca
2.82
2.76
2.82
2.20
1.84
1.74
1.64
1.78
1.38
2.33
1.60
1.42
Mg
0.39
0.35
0.33
0.33
0.40
0.34
0.39
0.36
0.50
0.55
0.53
0.42
K
1.79
1.53
1.65
1.75
1.80
1.69
1.87
2.14
2.04
1.93
2.06
1.66
Mn
39
43
49
103
231t
140t
268t
175t
214t
2l6t
230t
124t
Fe
73
210
35
200
51
111
55
84
129
81
229
43
Cu
7
6
3
9
5
4
5
6
6
7
10
3
yg/g
B
46
24
143tt
285tt
72
46
lOOtt
345tt
21
136
99tt
222tt
Al
40
51
29
25
38
31
74
39
295
51
59
32
Zn
45
40
38
29
62
67
98
43
69
52
78
52
Na
10
10
12
5
16
16
21
15
14
27
23
17
*Bulk samples of soil material were obtained from these depths for greenhouse study.
tManganese toxicity occurred.
ttBoron toxicity occurred.
-------
Table 118. Average Plant Weights and Chemical Composition of Bean Plants from Greenhouse Experi-
ment—One Inch Area Soil (55)
tN)
-P*
G-)
Soil*
material
0 - 1'
1 - 2'
2 - 3'
Boron
treatment
conc'n
mg/1
0.0
0.5
5.0
10.0
0.0
0.5
5.0
10.0
0.0
0.5
5.0
10.0
Plant
weight
grams
4.19
4.79
4.62
4.61
0.80
0.27
0.36
0.56
0.48
0.60
0.53
0.31
Plant tissue content
%
P
0.23
0.23
0.18
0.24
0.14
0.10
0.14
0.10
0.07
0.09
0.10
0.11
Ca
2.38
2-. 51
2.22
2.46
1.54
1.04
1.56
1.05
0.92
0.85
0.52
0.54
Mg
0.47
0.42
0.44
0.50
0.34
0.37
0.38
0.39
0.38
0.39
0.30
0.32
K
1.85
1.90
1.47
1.75
1.32
1.20
1.80
1.32
1.53
1.29
1.28
1.25
Mn
29
28
111
47
lOlt
194t
163t
20 7t
126t
184t
75t
118t
Fe
63
60
32
61
88
297
103
176
102
73
155
149
Cu
6
7
5
7
5
8
8
8
5
6
8
9
Pg/g
B Al
23 41
27 37
64 30
193 25
18 45
24 49
I29tt 51
275tt 47
95 260
26 109
109tt 63
205tt 188
Zn
53
41
40
59
41
55
65
76
71
62
60
60
Na
33
10
15
11
28
18
12
20
28
14
28
3
*Bulk samples of soil material were obtained from these depths for greenhouse study.
tManganese toxicity occurred.
ttBoron toxicity occurred.
-------
Table 119. Average Plant Weights and Chemical Composition of Bean Plants from Greenhouse Experi-
ment- -TWo Inch Area Soil (55)
ts>
Boron
treatment
Soil* conc'n
material mg/1
0 - 1'
0.0
0.5
5.0
10.0
1 - 2'
0.0
0.5
5.0
10.0
2 - 3'
0.0
0.5
5.0
10.0
Plant
weight
grams
6.35
5.79
5.40
4.74
1.19
0.95
1.47
1.29
0.51
1.03
0.51
0.46
Plant tissue content
P
0.19
0.25
0.21
0.27
0.13
0.14
0.13
0.11
0.07
0.08
0.11
0.10
Ca
2.30
2.28
2.35
2.48
2.20
1.99
2.07
1.88
0.86
1.06
1.71
0.88
Mg
0.52
0.54
0.46
0.40
0.48
0.43
0.49
0.42
0.41
0.48
0.53
0.46
K
2.08
1.68
1.92
1.96
2.25
1.87
2.21
2.36
1.35
1.82
1.94
1.69
Mn
177
43
84
46
373f
221t
453t
32 3t
245t
431t
346t
470t
Fe
63
64
64
70
96
52
90
81
90
308
80
64
Cu
5
6
5
7
7
5
7
6
6
5
7
6
B
172
37
113tt
295tt
33
77
209tt
307tt
19
30
163tt
332ft
Al
26
25
30
19
101
38
65
47
85
229
81
78
Zn
66
47
53
52
59
46
110
92
56
100
101
80
Na
13
12
11
13
32
15
24
21
16
47
20
27
*Bulk samples of soil material were obtained from these depths for the greenhouse study.
tManganese toxicity occurred.
ttBoron toxicity occurred.
-------
Table 120. Effect of Boron Treatment and Source of Soil on Dry Weight
(grams) of Bean Plants in Greenhouse Experiment (55)
Ave.
Ave.
Boron treatment
Solution concentration--mg/1
0.0 0.5 5.0 10.0
Total, boron added--ug/g of soil
0.000 0.323 3.230 6.460
Effluent Area
0"
1"
2"
Soil Depth: 0 -
6.09
4.27
6.41
5.74
4.83
5.84
4.75
4.68
5.44
1 foot
3.25
4.63
4.77
4.96a-/
4.60a
5.62b
5.59c
5.47bc 4.96b
4.22a
1.41a
1.47a
1.20a
1.14a
5.06c
Effluent Area
0"
1"
2"
Soil Depth: 1 -
2.09
0.88
1.27
2.99
0.36
1.05
1.66
0.42
1.50
2 feet
1.43
0.58
1.40
2.04c
0.56a
1.30b
1.30b
Effluent Area
Ave.
0"
1"
2"
Ave,
(all values)
1.56
0.50
0.56
0.87a
2.62a
Soil Depth: 2 -
1.72
0.64
1.07
1.14a
2.69a
1.45
0.59
0.54
0.86a
2.34a
3 feet
0.89
0.36
0.55
0.60a
1.98a
1.40b
0.52a
0.68a
0.87a
— Values in the same row or column without a common letter are
significantly different, P - 0.01, using Duncan's multiple range
A***. A^H *
test.
245
-------
Table 121. pH and Water Soluble Manganese Content of Soil from
Pots Used in Greenhouse Study. (55)
Water soluble
Mn
Soil depth pH ug/g
0
1
2
- 1'
- 2'
- 3'
Control area
5.6
5.0
4.8
0.269
0.524
0.817
1" effluent/week soil area
0 - I1 5.8 0.222
1 - 2' 4.8 0.525
2 - 3' 4.7 0.503
2" effluent/week soil area
0 - 1' 5.8 0.099
1 - 2' 5.2 1.738
2 - 3' 4.8 3.451
246
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Table 122. Effect of Boron Treatment and Source of Soil on Boron
Content (yg/g) of Bean Plants in Greenhouse Experiment (55)
Soil material
source
Effluent Area
0"
1"
2"
Ave.
Effluent Area
0"
1"
2"
Ave.
Effluent Area
0"
1"
2"
0.0
46.7
22.7
171.7
80. 3a
72.3
18.0
33.3
41. 2a
21.7
94.7
19.3
Boron treatment mg/1
0.5 5.0 10.0
Soil Depth: 0
24.0 143.3
26.7 63.7
37.0 113.0
29. 2a 106. 7a
Soil Depth: 1
46.3 100.0
24.3 129.0
78.7 208.7
49. 8a 145. 9b
Soil Depth: 2
136.3 99.3
26.0 109.0
30.0 163.0
- 1 foot
285.5
193.3
295.0
257. 8b
- 2 feet
345.3
275.0
307.0
309. Ic
- 3 feet
222.0
205.0
332.0
Ar-T — m
Ave.
124.41^
76. 6a
154. 2b
118. 4a
141. Oa
111.6a
156. 9a
136. 5a
119. 8a
108. 7a
136. 2a
Ave.
Average
(All values)
121.6a
55.6a
47.7a 125.4a 273.3b
- Values in the same row or column without a common letter are
significantly different at P = 0.01 using Duncan's multiple
range test
247
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Table 123. Autoclave-Extractable Boron Content of Soil Materials
Used in Greenhouse Experiment--yg/g (55)
Soil material
source Effluent Level - inches/week
Depth
feet 0.0 1.0 2.0
0-1 0.063a- 0.178b 0.215b
1 - 2 O.OOOa 0.002a 0.023a
2-3 O.OOOa O.OOOa O.OOOa
Ave. 0.021a 0.059b 0.079c
Effluent Level - inches/week
Depth
feet
0 - 1
1 - 2
2 - 3
0.0
O.OOOa
O.OOOa
1.0
0.178b
0.002a
O.OOOa
2.0
0-215b
0.023a
O.OOOa
Ave.
O.lSlb
O.OOSa
O.OOOa
— Values in the same row without a common letter are significantly
different, P = 0.01, using Duncan's multiple range test.
Values in the same column without a common letter are si
different, P = 0.01, using Duncan's multiple range test.
Adsorption Experiment. In the boron adsorption study, each of the nine
soil materials were equilibrated with seven concentrations of boron,
0.5, 1.0, 2.0, 5.0, 10.0, 25.0 and 50.0 mg/1. Ten gram samples of each
soil were weighed out in 50 milliliter polypropylene centrifuge tubes.
Twenty milliliters of the boron solutions were added, the tubes stop-
pered and then shaken in a mechanical shaker for twelve hours. The
samples were then centrifuged 5 minutes at 2000 rpm in an International
No. 2 centrifuge. An aliquot of the clear supernatant was analyzed for
boron by the Carmine Red Method.
Plots of Langmuir adsorption isotherms indicated a bi-modal adsorption
pattern with breaks in the curves occurring at equilibrium concentra-
tions ranging from 4 mg./l. to 20 mg./l. Biggar and Fireman (79)
found similar deviations in their Langmuir plots at concentrations
ranging from six to 26 mg. B per liter.
248
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The boron adsorbed by the nine soil materials equilibrated with the
5.0 mg B/l. solution typifies the differences between the soil materi-
als, Table 124. Although the control soils would have been expected
to have the largest adsorptive capacity, since that area had not been
receiving the boron, such was not the case. Instead the 1-inch treat-
ment area had the largest adsorptive capacity. However the 2-inch
treatment area which had been receiving the largest amounts of boron
in the applied wastewater did have the least adsorptive capacity when
averaged over all three depths. In seeking a possible explanation
for this anomalous situation, the soils were extracted with dithionate-
citrate solution to determine the relative quantities of free iron
oxide since Hatcher et al (57) had shown that sesquioxides were very
important in fixing boron. Table 125 indicates that B adsorbed from
the 5.0 mg B per liter solution was strongly correlated with the
extractable Fe203. The 1-inch wastewater treatment area which had
the highest average boron adsorptive capacity also had the largest
content of extractable Fe^. This appears to be a reasonable explana-
tion of its anomalously high boron adsorptive capacity.
Table 124. Boron Adsorbed by the Soil Materials Equilibrated with the
5.0 mg/1 Solution (55)
Boron adsorbed--yg/g
Effluent level inches/week
Soil depth 0 1 2 Ave.
0 -
1 -
2 -
Ave,
1'
2'
3'
i
1.06
2.54
4.30
2.64b
4.06
5.74
5.96
5.26c
1.50
1.90
2.36
1.92a
2.22al/
3.38b
4.22c
— Values in the same row or column without a common letter are
significantly different, P = 0.01 using Duncan's multiple range
test.
249
-------
Table 125. Dithionate-Citrate Extractable Fe203 and Boron Adsorptive
Capacity of the Nine Soil Materials from the Three Waste-
water Treatments. (55)
Soil
0
0
1
1
2
2
0
1
2
Depth
- 1'
- 1'
- 2'
- 2'
- 3'
- 3'
- 1'
- 2'
_ 7t
Wastewater
Level
in. /week
0
2
0
2
2
0
1
1
1
Extractable
Fe203
%
0.83
1.07
1.25
1.43
1.54
1.68
2.13
2.37
2.39
Boron , /
Adsorbed^7
mg B/kg soil
1.06
1.50
2.54
1.90
2.36
4.30
4.06
5.74
5.96
— From the 5.0 mg B per liter solution.
250
-------
Oxygen Relationships
Previous Work. Treated sewage effluent was applied to agronomic
cropland to achieve renovation and to increase the recharge of the
ground water reservoir. Amounts applied were 0, 1.0 and 2.0 inches
at weekly intervals for approximately 25 consecutive weeks.
Mien such large amounts of effluent are applied to a soil, some changes
in the natural soil environment can be expected. Of great concern is
the nature of the change in the aeration status of the soil. Pore
space containing the gaseous phase is filled to a large extent by the
liquid phase and thereby could alter the interchange of gases between
the atmosphere and the soil as well as within the soil itself.
Aerobic conditions must prevail in the upper soil zone to maintain
proper root function and desirable organic matter transformations.
Since treated sewage effluent is relatively high in nitrogen it is not
inconceivable that possible pollution of the ground water reservoir
could result if conditions were favorable for nitrification. To pre-
vent this, it would be desirable to stimulate denitrification in the
deeper layers of the soil and thereby convert the excess nitrate to
molecular nitrogen and minimize the .reduction of iron and manganese,
or permit their subsequent reoxidation in a cyclic system.
Lemon and Erickson (86a) in characterizing soil aeration with the
platinum microelectrode noted that oxygen concentration at the root
surface should increase as soil water tension increases because as
water contents diminish, additional pore space is available for
gaseous oxygen diffusion (86).
The critical oxygen diffusion rate (O.D.R.) of soils in which roots
of many plants will not grow does not appear to be sharply defined.
Stolzy and Letey (83) reported that an O.D.R. value of 20 x 10~°g'
cm~2'jnin~l appeared to be critical for the root growth of many plants.
However, Van Diest (84) found no yield differences in top growth of
corn due to differences in soil O.D.R. values ranging from a low of
10 x 10"8g cm"2 min"1 on compacted soil to a high of 50 x 10"8g-cm"z-
min'l on well aerated soil.
Cannon (85) in working with 30 plant species noted that when oxygen
was entirely absent from the soil in which the roots were growing,
growth ceased in all species. The oxygen concentration for normal
growth was temperature dependent, being higher in higher temperatures.
Wiegand and Lemon (86) calculated a critical oxygen concentration in
the liquid film at the root surface of onion root segments to be 4.45 x
10'6g cm'3. This is equivalent to 12% oxygen in the gaseous phase and
they suggested that this is a conservative estimate of the critical
oxygen concentration for other roots.
251
-------
Many changes taJce place in a soil when it is subjected to continual
wetting. Not only are oxygen concentrations diminished but also the
appearance of reduced forms of nitrogen, iron and manganese becomes
important.
Although the effects of moisture on denitrification are not clearly
understood, Allison et. al. (87) and Jones (88) concluded that the
effect of moisture in soils is primarily one of reducing the volume of
air filled pores with a consequent reduction in oxygen concentration.
Miller and Johnson (89) and Patrick and Wyatt (90) both demonstrated
large losses of nitrogen when soils were subjected to low tensions or
submergence.
When soils are waterlogged and the partial pressure of oxygen declines,
manganese is reduced to the more soluble manganous form. Piper (91)
showed that waterlogging a soil for a week had about the same effect
on the yield and manganese content of the plants as did the application
of manganese sulfate at a rate of 5 cwt per acre. The increase in
soluble manganese brought about by waterlogging has also been reported
by Godden and Grimmett (92) who showed that plants grown in undrained
pots were very much richer in manganese than those grown in drained
pots.
The behavior of iron in the soil is similar to that of manganese.
Should anaerobic conditions prevail, the amount of the reduced form of
iron rapidly increases. Godden and Grimmett (92) pointed out that
under conditions favorable to soil aeration and leaching, the total
amount of soluble iron in the soil at any one time is small. Similar
results were reported by Islam and Elahi (93) who found that the amount
of ferrous iron gradually increased and remained practically constant
after about three weeks of waterlogging.
Site Description and Procedures. The experimental area consisted of
18 acres in a 2 year rotation of hay and corn. Experimental locations
were in a contour strip arrangement. The study sites were in pairs
with respect to application rates but individual with respect to crop
times application rate. Laterals running from the main irrigation
line were 80 feet apart. The sprinklers were spaced at 80 foot inter-
vals along the laterals in a triangular network.
Within each experimental site, measurement of oxygen diffusion and
oxygen concentration were recorded at five different depths, 3, 6, 12,
18 and 24 inches. Installations at each depth included ten platinum
microelectrodes, 3 oxygen concentration chambers, a thermistor for
recording soil temperature and a tensiometer or Bouyoucos moisture
block for determining soil moisture content. Two porous cup suction
lysimeters placed at 6 and 24 inches were installed for the collection
of water samples. A size No. 10 can was placed at each location to
record the amount of effluent that had been applied and to obtain a
composite sample of the effluent.
252
-------
The oxygen diffusion apparatus used was similar to that described by
Van Doren and Erickson (Mimeo report: Technique for measuring the
rate of oxygen diffusion through the soil with the platinum micro-
electrode. 1958. Dept of Soils, Michigan State Uhiv, Lansing, Mich)
and was obtained from Dick's Machine and Tool Co, Lansing, Mich. The
platinum microelectrodes were 22 gauge and the potential applied was
-0.65 volts. The diffusion current in microamperes was converted to
O.D.R. values (gO? x 10-8 an'? sec"1) by multiplying by 5.93. The
microelectrodes of various lengths are shown in Figure 68.
Because it proved difficult to continually reinsert 22 gauge wire up
to depths of 24 inches without badly damaging the electrodes, all
electrodes were permanently placed. Initial random insertion of the
microelectrodes was carried out by first driving a steel rod, whose
diameter was slightly larger than that of the insulated portion of
the electrode, to within 1 inch of the desired depth. The electrode
was then placed in the pre-made channel and pushed the remaining inch
into new soil, insuring a good seal. The soil was then tamped around
the protruding electrode lead wire.
At the close of the investigation, electrodes at the 3 and 6 inch level
at six locations were pulled and cleaned with 0000 steel wool (the
abrasive action polishes the platinum surface, removing any poisonous
substances), and reinserted in the same vicinity. After 5 minutes, to
insure steady state conditions a new measurement was made. The two
mean values at each location at each depth were compared to determine
if poisoning was a problem. In only one of the twelve cases were the
means significantly different and indicative that "poisoning" had
occurred. It was therefore assumed that leaving the microelectrodes
in place over a four-week period was an acceptable technique.
The oxygen concentration apparatus consisted of an oxygen sensor, (YSI
Model 52) and a recycling mechanism consisting of two hypodermic needles
(intake and exhaust) and a rubber bulb to circulate the gases from the
diffusion chamber, inserted in the soil, through the oxygen sensor.
The meter readout values of percent oxygen were corrected on the basis
of known volumes of the analyzer and chamber to give actual percent
oxygen in the chamber alone.
The oxygen diffusion chambers were made from aluminum tubing of various
diameters cut to desired lengths. The bottom of the chamber was closed
by a disc of aluminum window screening. The upper end was closed with
a rubber stopper through which protruded a short section of h inch
copper tubing topped by a rubber septum. Each chamber was brought to
a constant internal gaseous volume of 200 ml by including various
amounts of solid glass rods within the chamber. The chambers used at
the several depths are shown in Fig. 68.
253
-------
I J
L '
*»
Figure 68. Platinum MLcroelectrodes and Oxygen Concentration Chambers,
-------
Chamber placement was achieved by first drilling a hole with a portable
power auger to the desired depth. The chamber was then pushed into
place. The voids between the chamber and the hole were filled with
silica flour to insure a tight fit, and clay soil material was used to
make a firm seal at the surface.
A series of determinations of physical soil properties relevant to this
investigation were made by using soil cores. These cores were collect-
ed with a Uhland core sampler. Soil samples were obtained at the 3,
6, 12, 18 and 24 inch levels. Samples were subjected to tensions of
50, 100, 200, 400, 800 and 1000 cm of water on a pressure plate appara-
tus. Total pore space was determined from the dry bulk density. Water
filled capillary pore space and aeration pore space was determined for
each tension. A separate soil sample at each depth was secured and
used to calibrate the Bouyoucos moisture blocks.
To keep the concentration of nitrogen, iron and manganese under constant
surveillance, soil water samples were taken and analyzed on a weekly
basis throughout the course of the experiment.
Installation of the porous cup suction lysimeters was much like that
of the oxygen chambers. The lysimeter was inserted in a pre-drilled
hole after a layer of* silica flour had been placed at the bottom to
insure good contact with the porous cup. To minimize leakage along the
plastic tubing to the porous cup, silica flour was poured around the
outside of the tubing and the soil at the surface was mounded and tamp-
ed against the protruding tubing. The lysimeters were evacuated to an
internal pressure of approximately 1/3 atmosphere prior to irrigation
by using a vacuum pump. When irrigation ceased the internal vacuum
was relieved and the soil water removed from the lysimeter chamber by
a suction siphon arrangement. In the control area an attempt was made
to obtain samples after each rain but in most cases the soil water
tension was so great that only one- third as many samples were obtained
as in the effluent treated areas.
Nitrogen analyses included the quantitative determination of
NOj'-N and N02~-N. Ammoniacal nitrogen was analyzed according to a
modification of the Nessler procedure (94) . Nitrate nitrogen determin-
ations were made using brucine as described in the Standard Methods for
the Examination of Water and Waste Water (20) . Nitrite nitrogen was
determined using 1-naphthylamine . HC1 (20) . The total amounts of iron
and manganese were determined as follows. A 50 ml water sample was
evaporated to dryness at 150°C, the residue dissolved in 0.1N HC1, and
then analyzed with a Perkin-Elmer Atomic Adsorption Spectrophotometer.
The crops occupying the land in this experiment were hay and com (Zea
mays) . Originally alfalfa Qfedicago sativa) was planted, but after
two years, the stand in the 1 and 2 inch treatment areas became largely
255
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crowded out by timothy (Phleum pratense), quackgrass (Agropyron
repens), and a variety of weeds. However, there was still a good stand
of alfalfa in the control area. The corn location consisted of two
varieties, one for silage (Pa 602A) and the other for grain (Pa 444).
The silage variety occupied approximately one-third of the contour
strip and was planted in 19 inch rows. The remaining two-thirds of the
strip containing the grain variety was divided into equal widths of 19
and 38 inch row spacings. The experimental sites were located in the
38 inch row spacing area.
All statistical analysis was carried out on the IBM-7074 computer and
the Duncan's multiple range test was used to define significance of
the differences between variables.
Oxygen Diffusion Rates (P.P.R.). The analysis of variance for the
O.bTR. data showed that the only main factors that proved to be sig-
nificant, were crop and depth of sampling. The only interaction of
importance, which proved significant, was "irrigation treatment" versus
"day after cessation of irrigation". The nature of this interaction
being that "day-3" O.D.R. values were significantly larger than' "day-1"
values on the irrigated sites but not on the control site.
Although O.D.R. decreased with an increase in the amount of applied
irrigation, the difference was not significant (Table 126).
Soil moisture data taken at the time of each weekly sampling showed
that the control area generally contained less water on a volume basis
than did the effluent areas. The 1.0 and 2.0 inch effluent treatment
areas were usually above or near field capacity at all depths while
the control areas were only at or above field capacity at the 24 inch
depth.
Oxygen diffusion rates were significantly higher in the corn areas than
in the hay areas. The difference between the two locations was due
largely to the higher O.D.R. in the upper 3 inches of the soil. The
loosening action of tillage in the corn locations was reflected in a
higher average total and aeration pore space.
Differences in O.D.R. among the time factors (succeeding weeks or days
after cessation of irrigation) were not significant. During the test
period, soil moisture contents did not change appreciably from week to
week' or from day-1 to day-3 after cessation of irrigation. With almost
constant soil moisture contents, O.D.R. would not be expected to change
s ignificant ly.
The O.D.R. values at the 3 and 6 inch depths differed significantly
from the 12, 18 and 24 inch depths. The differences in O.D.R. appear
to be associated with differences in aeration porosity of core samples
taken at the various depths.
256
-------
Table 126. Ranked Means in Ascending Order of the Main Factors of
Oxygen Diffusion Rate Experiment.*
O.D.R. x 168g on'2 min"1
Factors Level Mean
Effluent •
Treatment (in.)
Crop
Weeks
Depth (in.)
Day
2.0
1.0
0.0
Hay
Corn
1
4
2
3
18.0
12.0
24.0
3.0
6.0
i
3
19. 5a
19. 6a
22. 9a
18. 6a
22. 7b
19. 7a
20. 6a
20. 9a
21. 4a
14. 7a
17. 3a
17. 9a
26. 6b
26. 8b
19. 6a
21. 8a
* The values followed by the same letter are not significantly different
by the Duncan's multiple range test at the 5% level.
At a tension of 800 on of water, the average aeration pore space in the
3 and 6 inch zones was 15%, that in the 12, 18 and 24 inch zones was
only 131. At 50 cm tension, the respective aeration pore space values
were 101 and 8% in the upper and lower zones.
Oxygen Concentration. The extent to which soil air differs in oxygen
concentration from atmospheric air, is deteimined by the rate at which
it is replenished by diffusion. Soil water content is also important
because it affects diffusion.
The data in Table 127 indicate that all three effluent treatments were
significantly different from each other with oxygen concentration
decreasing as effluent treatment increased. The range in concentration
of oxygen was relatively narrow, 19.6% to 18.41, and even the smallest
mean would generally not be regarded as indicative of adverse aeration
conditions.
257
-------
Table 127. Ranked Means of the Main Factors of the Oxygen Concentration
Experiment.
Percent Oxygen
Factor
Treatment (in.)
Crop
Depth (in.)
Week
Level
2.0
1.0
0.0
Corn
Hay
3.0
6.0
24.0
12.0
18.0
8
4
2
6
5
3
7
1
Mean
18. 4a
19. Ob
19. 6c
18. 8a
19. 2a
18. 4a
18. 6a
19. 2b
19. 2b
19. 4b
18. la
18. 4a
18. 6a
18. 8a
19. 3a
19. 5a
19. 5a
19. 6a
— The values followed by the same letter are not significantly
different by the Duncan's multiple range test at the 5% level.
Oxygen concentrations did not differ significantly between the two
crop locations or with time over the eight-week period but did differ
significantly with depth.
The depth effects were in some respects unorthodox in that oxygen
concentrations in the upper two zones were significantly smaller than
in the lower three zones. As a possible explanation one can assume a
diffusion system in which a normal vertical concentration gradient
(source gradient) would exist in the vertical aeration pore continuum
which in turn is imbedded in a vertical oxygen sink gradient, namely,
the microbial and root sinks. The gradient in the vertical aeration
pore continuum could be relatively small but the sink gradient could
change very abruptly. As a result of the interaction of the two
258
-------
gradients and the displacement of the vertical pore continuum by the
diffusion chamber it is conceivable that the oxygen concentration
distribution by depth shown in Table 127 could eventuate.
Nitrogen, Manganese and Iron Concentrations. The data in Table 128
indicate that significant differences occurred as a result of efflu-
ent treatment with respect to the nitrogen forms but not with respect
to the manganese or iron. The significant differences in the concen-
tration of nitrate, nitrite and ammoniacal nitrogen were due to the
2.0 inch level weekly application of effluent. Differences between the
control and 1.0 inch level of effluent treatment were not significant.
Table 128. Concentration of Various Forms of Nitrogen and of Manganese
and Iron in Soil Water Samples.*
Factor
NO! NOl
3 2
Level Nitrate Nitrite NH4 Mn Fe
Effluent
Treatment (in.)
Crop
Depth (in.)
0.0
1.0
2.0
Corn
Hay
6.0
24.0
l.Oa
2.4a
6.1b
4.2b
3.2a
3.0a
4.4b
0.017a
0.030a
0.056b
0.024a
0.052b
0.042a
0.035a
0.35a
0.40a
1.28b
0.67a
0.82a
O.Sla
0.68a
0.07a
O.OSa
0.06a
0.04a
O.OTb
0.03a
0.08b
0.09a
O.OSa
0.07a
0.07a
O.OSa
O.OSa
0.06a
* Within any factor grouping mean values followed by the same letter
are not significantly different by the Duncan's multiple range test
at the 5% level.
With respect to crop locations, nitrate was significantly higher under
corn and nitrite concentration was significantly higher under hay.
Crop location differences were not significant with respect to ammoni-
acal nitrogen.
The significantly higher nitrate levels under corn were primarily a
reflection of the higher nitrate levels under corn in the control and
1.0 inch effluent treatments. The significant crop x effluent treat-
ment interaction is evident in Table 129.
The significantly higher nitrite level under hay was primarily due to
the higher nitrite levels under hay on the two effluent treated areas.
259
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Table 129. The Crop x Effluent Interaction^ with Respect to Nitrate.
Nitrogen Levels in Suction Lysimeter Samples Averaged
Over Both Depths
Effluent Treatments - in. per week
0 1.0 2.0
Crop Nitrate nitrogen - mg per liter
Hay
Corn
0.2
1.9
1.1
3.8
6.7
5.6
— Interaction significant at P = 0.01
The crop x effluent treatment interaction in this case was significant
at the 51 level. It is pertinent to recall that the O.D.R. values
under hay were significantly lower than under corn and may have con-
tributed to a greater persistence of the nitrite which was being
applied in the effluent or to a greater production of nitrite.
The significantly higher manganese levels under hay was primarily due
to the higher manganese levels at the 24 inch depth under hay. The
crop x depth interaction was significant at the II level. Again, as
in the case of the nitrite, the significantly lower O.D.R. under hay '
may have contributed to greater persistence of the more soluble reduced
form of manganese.
Effects of depth of sampling were significant with respect to nitrate
and manganese but not with respect to iron, nitrite or ammoniacal
nitrogen.
Mean concentrations of nitrate, nitrite, and ammoniacal nitrogen and
of manganese and iron in the applied sewage effluent during June, July
and August were 4.6, 0.20, 19.2, 0.14, and 0.16, respectively. In
comparing these values with the mean values in the soil water samples
it is apparent that passage of the effluent through the soil-crop sys-
tem substantially diminished the sum concentration of the nitrogenous
components and the manganese and iron.
O.D.R. and oxygen concentration data and the nitrite, manganese, and
iron values in the soil water samples indicate that aerobiosis is being
maintained in the upper 24 inches, hence denitrification cannot be
regarded as contributing substantially to nitrogen removal. Soil
analyses indicate no significant accumulation of ammoniacal nitrogen
in the effluent treated areas therefore it can be assumed that the
NI-N is being removed by the crop and soil microbes directly and/or
260
-------
being nitrified and then absorbed by the crop or microbes. The signi-
ficantly higher nitrate values in the 2.0 inch effluent treatment
indicate that the crops and microbes were not fully utilizing the
nitrogen supply. It should be pointed out, however, that the mean
nitrate-nitrogen concentration in the soil water was still substantial-
ly below the U.S. Public Health Service mandatory limit of 10.0 mg/1.
In conclusion the weekly interval between applications appears to be
suitable for maintaining aerobic conditions in the upper 24 inches
necessary for prevention of reduction of Fe and Mn, and for allowing
nitrification of ammoniacal forms and prevention of denitrification
on a large scale.
261
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SECTION VII
FORESTED AREAS
Soil Percolate Water Quality
Samples of percolating water were collected at various soil depths in
the forested areas during the period 1963 to 1969. Only results of
the 1969 analyses are discussed here, however, all data collected dur-
ing the earlier years are shown in Tables A-23 to A-42 in the Appendix.
The chemical composition of the sewage effluent applied to the Farm
Woodlot Site in 1969 is shown in Table 130. Weekly variations in
concentration of constituents are shown by the range between maximum
and minimum values. Total amounts of each constituent applied at the
2-inch per week rate are also shown in Table 130. The fertilizer
value of the effluent is readily evident in that the 2-inch applica-
tion provided commercial fertilizer constituents equivalent to approx-
imately 271 pounds of nitrogen, 151 pounds of phosphate, ^205), and
210 pounds of potash (K?0). This would be about equal to applying
2000 pounds of a 13-8-10 fertilizer.
The average concentrations of constituents in the percolate samples
for various soil depths on the irrigated and control plots at the Farm
Woodlot Site are shown in Tables 131 and 132. The average composition
of water samples obtained at various depths indicated that after 7
years of operation, during which approximately 34 feet of wastewater
had been applied in the 2-inch per week treatments, the renovation
capacity of the biosystems was still satisfactory, except in the 2-inch
red pine area where nitrate concentrations were above desirable levels.
The first stage of renovation in the forested areas occurs during
passage of the effluent through the forest floor. Concentrations of
MBAS (detergent residual) were reduced by approximately 55 percent.
MBAS analyses were not made where small volumes of percolate were
obtained because previous results indicated a consistently high degree
of renovation. For instance, results in 1968 indicated that percola-
tion through the upper 4 feet of soil decreased average concentrations
by 78 to 81 percent. These data indicate that the relatively thin and
highly permeable forest floor layer has a high adsorptive capacity and
biological degradation capacity for the detergent residue. It should
also be noted that the methylene blue process used to determine the
MBAS concentration indicates only the apparent concentration since both
organic and inorganic anions commonly found in soils give positive
errors in the analysis. This is evident in the results of the analysis
of percolate collected from the control plots, which indicated an
average apparent MBAS concentration ranging from 0.12 to 0.17 mg/1
(Table 132). Since the concentrations of MBAS in percolating water
leaving the forest floor are only in the magnitude of approximately
0.17 mg/1, the percent renovation may actually be considerably higher
than that indicated.
263
-------
Table 130. Chemical Composition of Sewage Effluent Applied on the
Experimental Plots (Faim Woodlot Site) During the Period
.April 15, 1969 to October 29, 1969.
Constituent
PH .
MBASl/
Nit rate -N
Organic-N
NH4-N
Phosphorus
Potassium
Calcium
Magnesium
Sodium
Chloride
Boron
Manganese
Range
Min
mg/1
7.1
0.1
0.0
0.0
0.0
0.821
6.7
18.2
9.4
22.5
8.7
0.2
0.0
Max
mg/1
8.3
1.2
12.5
16.5
32.5
17.143
20.8
34.0
17.7
59.5
68.7
0.4
0.2
Ave
mg/1
7.8
0.4
5.4
6.4
9.5
4.606
13.5
28.0
14.3
38.1
43.2
0.3
0.1
Total amount
applied!/
Ib/acre
5
70
82
123
66
175
363
185
494
560
4
1.3
— Methylene blue active substance (detergent residue).
2/
— Amount applied on plots which received 2 inches of effluent per
week.
Results in Table 131 also indicate that the "living filter" was highly
efficient in removing phosphorus, one of the principal nutrients
responsible for eutrophication. Phosphorus concentrations at the 2-
foot soil depth were reduced by 97 to 99 percent. Phosphorus concen-
trations of percolating water samples taken from deep groundwater wells
indicated that phosphorus concentrations of percolating water at the
4-foot depth on the control plots ranged from 0.05 to 0.07 mg/1. These
values are not very different from the irrigated plots considering that
34 feet of sewage effluent with phosphorus concentrations ranging from
6 to 10 mg/1 have been applied to the plots over a 7-year period.
Phosphorus concentrations have increased in the treated areas, particu-
larly at the 6-inch depth. As shown in Tables 130 and 131 the average
concentrations in the treated areas ranged from 0.056 to 0.261 mg/1,
whereas, in the control areas the average concentrations only ranged
from 0.020 to 0.051 mg/1. Phosphorus concentrations in percolating
water have fluctuated at any one depth from year to year but the general
trend is for the average concentration to diminish with depth (Figures
6§, 70, 71, and 72,
264
-------
Is)
ON
cn
Table 131. Average Concentration of Constituents in the Percolate Water Samples Collected from
Tension Lysimeters in the Effluent Treated Plots at the Farm Woodlot Site During the
Irrigation Period April 15 to October 29, 1969.
Plot and No. of Weekly
soil depth samples application pH
MBAS
NO
3'N
Org-N
NH4-N Cl P Na K Ca Mg Mn
B
Concentration in rag/liter
Effluent
Quality
Hardwood
F.F. 2/
6 indies
24 inches
48 indies
Red Pine!/
F.F.
6 inches
12 inches
24 inches
48 inches
Red Pine!/
F.F.
6 inches
12 inches
24 inches
48 inches
27
28
10
5
15
23
19
16
5
7
16
14
5
9
11
7.
1
7.
7.
7.
7.
1
7.
7.
7.
7.
7.
2
7.
7.
6.
6.
6.
8
1
7
6
9
1
5
7
7
9
3
5
9
9
4
0.38
0.13
I/
T/
0709
0.16
I/
T/
T/
T/
0.22
I/
T/
T/
T/
5
11
6
4
7
11
17
14
9
4
10
10
12
19
24
.4
.6
.8
.9
.2
.7
.6
.4
.0
.2
.0
.5
.7
.6
.2
6.4
2.6
0.9
1.2
1.0
4.6
1.0
0.7
0.7
1.1
4.6
2.1
1.1
1.0
0.3
9.5
3.3
1.1
0.9
1.1
3.8
1.1
1.2
0.5
0.6
5.6
1.5
0.5
1.1
0.9
43.
29.
36.
89.
36.
31.
31.
24.
25.
55.
48.
21.
27.
34.
61.
2 4.060 38.1 13.5 28.0 14.3 0.08
0 3.913 21.5 14.3 24.3 9.5 0.19
3 0.212 37.4 5.7 30.6 24.8 0.03
2 0.065 59.5 8.2 27.9 21.7 0.05
0 0.047 51.1 5.8 33.9 28.4 0.03
7 3.537 24.6 14.0 22.5 9.2 0,14
6 0.056 32.9 10.9 33.4 27.2 0.04
7 0.129 27.9 9.3 49.8 24.7 0.03
6 0.068 I/ I/ I/ I/ I/
6 0.064 4¥.2 5.5 35~.3 26~.6 0703
4 4.352 41.7 21.4 27.9 13.4 0.42
7 0.261 21.1 11.9 34.9 17.0 0.06
8 0.111 37.6 8.2 17.5 6.9 0.18
3 0.040 41.7 3.7 15.9 6.2 0.06
8 0.037 41.1 2.1 5.3 2.8 0.21
0.28
0.21
0.31
0.37
0.04
0.19
0.21
0.20
I/
0706
0,24
0.29
0.32
0.20
0.10
-------
Table 131. Continued.
Plot and No. of Weekly
soil depth samples application pH
MBAS N03-N
Org-N
NH4-N
Cl
P
Na
K Ca
Mg Mn
B
Concentration in mg/liter
Old Field
6 inches
12 inches
24 inches
48 inches
11
21
5
11
2
7.4
7.7
7.6
7.7
I/ 7.3
0.03 2.8
I/ 8.3
T/ 2.3
2.4
1.0
2.1
1.3
1.2
0.8*
1.5
0.9
31.9
25.2
24.5
28.0
0.293
0.057
0.122
0.098
33.7
38.4
42.9
49.6
3.3 20.9
3.4 35.2
5.3 29.8
5.7 21.2
12.6 0.03
20.6 0.03
18.6 0.04
17.7 0.07
0.24
0.25
0.28
0.21
~ Not determined.
g} —' Forest Floor (1.5 to 2.0 inches thick).
— Irrigated with rotating sprinklers on 42-ft risers, 1963-1967 and on 5-ft risers thereafter.
-------
ts)
0.5
0.4 _
0.3
a. O.2
O.I
. 6 inch
. 12 inch
. 48 inch
1965
1966 1967
year
1968
1969
Figure 69. Msan Annual Phosphorus Concentration in Suction Lysimeter Samples at Three Depths
in the Hardwood Area on Hublersburg Soil Which Received One Inch of Wastewater at
Weekly Intervals. 1965-1969
-------
0.6
0.5
0.4
0.3
9
E
a. 0.2
O.I
— 6 inch
... 24 inch
__ 48 inch
_L
J_
1965 1966 1967 1968 1969
year
Figure 70, J*fekn Annual Phosphorus Concentration in Suction
Lysimeter Samples at Three Depths in the Red Pine
Area on Hublersburg Soil Which Received One Inch of
Wastewater at Weekly Intervals. 1965-1969
268
-------
0.4 -
0.3 -
6 inch
_ 24 inch
.. 48 inch
Q. 0.2 _
O.I _
1969
Figure 71. Msan Annual Phosphorus Concentration in Suction
Lysimeter Samples at Three Depths in the Red Pine
Area on Hublersburg Soil Which Received IWo Inches
of Wastewater at Weekly Intervals. 1965-1969
269
-------
0.5
0.4
03
0.2
o»
i
a.
O.I
6 inch
12 inch
— 48 inch
1965
1966
1967
1968
1969
y«ar
Figure 72. Msan Annual Phosphorus Concentration in Suction Lysimeter Samples at Three Depths
in the Old Field Area on Hublersburg Soil Which Received Two Inches of Wastewater
at Weekly Intervals. 1965-1969
-------
Nitrogen, like phosphorus, is one of the elements responsible for
eutrophication and the profuse growth of aquatic plants in streams.
After 7 years, nitrate-nitrogen concentrations in percolating water
at the 4-foot soil depth ranged from 2.3 to 24.2 mg/1 (Table 131) and,
except for the red pine, 2-inch plot, were below the U.S. Public Health
Service recommended drinking water limit of 10 mg/1. Concentrations
of nitrate-nitrogen in percolating water at the 4-foot depth on the
control plots ranged from 0.1 to 0.5 mg/1. Nitrate-nitrogen concentra-
tion of the groundwater as measured at deep wells on the site remained
below 3 mg/1.
Increasing concentrations of nitrate-nitrogen in the forested areas
receiving continued irrigation with sewage effluent could become a
major problem and a deterrent to long-term use of forested areas for
disposal sites. One possible way to reduce the nitrate concentration
is through denitrification, a microbiological process that occurs when
biodegradable organic material and nitrates are combined under anaero-
bic conditions. Certain bacteria use the oxygen of nitrates in their
metabolism, thereby reducing the nitrates to nitrogen and nitrogen
oxides, which escape to the atmosphere. To create conditions favorable
for biodenitrification, drainage periods between irrigation should be
long enough to allow aeration in the upper soil horizons. When ni-
trates and biodegradable organic material reach the deeper soil
horizons denitrification should occur if denitrifying organisms are
present and anaerobic conditions exist.
The average concentrations of Na, K, Ca, Mg, Mn and B were increased
or decreased in variable amounts in the upper soil horizons. Average
concentrations of manganese were quite similar on irrigated and control
plots (Tables 131 and 132). Whereas, average concentrations of boron,
potassium, calcium, sodium, magnesium and chloride were considerably
higher on the irrigated plots. They may cause a slight increase in
total salinity but the groundwater would still easily meet drinking
water quality standards.
In addition to the red pine plots which were initially irrigated with
rotating sprinklers over the canopy oil 42-foot risers a second area
(designated as New Red Pine) was irrigated with sprinklers under the
canopy on 5-foot risers. Irrigation of this plot was initiated in
July 1964. Results for 1965 to 1968 are given in Tables A-35 and A-36
in the Appendix. Results for 1969 for this area are presented in
Table 133. Although this area has only been treated during 6 years
rather than 7 years there appears to be no large differences in terms
of renovation of the wastewater between the two methods of application.
In terms of efficiency in operation and maintenance, the shorter risers
are more desirable.
Another mixed hardwood, 3 acre plot designated as New Gamelands Area
was established in November, 1965 and has received an application of
271
-------
tsJ
Table 132. Average Concentration of Constituents in the Percolate Water Samples Collected from
Tension Lysimeters in the Control Plots at the Farm Woodlot Site During the Period
April 15 to October 29, 1969.
Plot and No. of Weekly
soil depth samples application pH MBAS NOj-N Org-N NH4-N Cl P Na K Ca Mg Mn B
Concentration in rag/liter
Hardwood
F.F.2/
6 inches
12 inches
24 inches
48 inches
Red Pine
F.F.
6 inches
12 inches
24 inches
48 inches
Red Pine
F.F.
6 inches
12 inches
24 inches
48 inches
16
12
6
12
7
16
6
7
4
1
16
6
9
6
9
1
6.6
7.7
7.7
7.3
6.6
1
6.5
7.8
7.8
7.9
7.6
6.5
7.8
7.7
7.7
6.9
0.17
I/
0702
0.04
!/
0.12
I/
T/
I/
0.12
I/
T/
T/
T/
3.9
0.4
0.4
0.3
0.1
6.7
0.1
0.1
0.2
0.2
6.7
0.6
0.3
0.1
0.5
3.6
1.7
2.0
1.1
1.8
3.2
1.1
1.0
1.1
1.4
3.2
1.6
0.7
0.9
0.6
2.1
0.6
1.5
1.6
0.6
2.4
0.3
0.4
0.4
0.4
2.4
0.9
0.7
0.4
0.4
0.4
1.8
1.3
2.4
1.6
0.6
1.0
0.4
0.8
0.9
0.6
6.6
7.9
19.7
15.3
0.347
0.023
0.082
0.025
0.072
0.338
0.020
0.037
0.040
0.010
0.338
0.051
0.047
0.034
0.050
0.4
1.3
1.5
2.3
3.6
0.5
1.1
1.1
2.7
I/
0.5
6.9
4.9
11.8
10.9
9.5 14.1 1.4 0.10
0.6 15.5 9.5 0.04
6.1 31.1 21.1 0.04
3.6 13.2 10.1 0.18
1.2 4.8 3.3 0.04
8.9 17.4 1.7 0.10
2.5 31.4 19.6 0.03
0.5 41.2 20.4 0.04
2.2 33.7 21.9 0.06
11 11 11 II
8.9 17.4 1.7 0.10
12.2 45.6 26.9 0.04
4.3 55.7 17.8 0.02
4.7 30.9 14.7 0.03
1.8 3.2 0.7 0.08
0.08
0.03
0.06
0.05
0.03
0.06
0.04
0.03
0.05
11
0.06
0.12
0.06
0.05
0.03
-------
Table 132. Continued.
Plot and No. of Weekly
soil depth samples application pH MBAS ND--N Org-N NH.-N Cl P Na K Ca Mg Mn B
Concentration in mg/liter
Old Field
6 inches
12 inches
24 inches
48 inches
13
6
2
15
2
7.7
8.1
7.9
7.3
I/
T/
T/
I/
0.4
0.2
0.4
0.2
2.6
2.6
1.4
0.8
1.0
0.9
0.7
0.6
0.3
0.3
0.2
0.4
0.036 1.5
0.099 1.5
0.288 1.0
0.051 1.9
2.6
7.6
0.4
1.8
37.4 21.9
51.4 27.1
39.6 18.8
2.7 0.8
0.02 0.05
0.03 0.08
0.08 0.05
0.05 0.03
— Not analyzed.
2/
-' Forest floor (1.5 to 2.0 inches thick).
-------
Table 133. Average Concentration of Percolate Samples Collected from Forest Floor Pans and Tension
Lysimeters in .the New Red Pine 2" Per Week Area During the Irrigation Period 4-15-69
to 10-29-29.£/
No. of
samples
pH MBAS N03-N Org-N NH4~N Cl
P
Na
K
Ca
Mg
m
B
Concentration in mg/1
Effluent Quality
Forest Floor Pans
6 inches
12 inches
24 inches
48 inches
27 .
27
26
21
25
22
7.8 0.48
7.2 0.15
7.5 0.11
7.7 0.09
7.7 I/
7.1 0.10
3.7
15.9
22.6
21.3
20.8
17.7
4.7
2.7'
0.8
1.1
0.8
1.0
14.4
3.5
1.8
1.4
1.5
0.8
43.6
38.9
34.3
32.8
37.5
33.7
5.784
4.924
1.700
0.446
0.316
0.250
35.2
32.3
32.2
31.3
40.8
31.8
13.5
15.5
13.3
8.3
4.6
5.2
27.7
23.9
44.1
55.0
47.1
14.7
13.8
11.5
27.1
30.1
27.9
10.4
0.16
0.05
0.03
0.03
0.02
0.11
0.31
0.22
0.26
0.24
0.20
0.16
— Not analyzed.
2/
— Irrigated with rotating sprinklers on 5 ft risers.
-------
2 inches of sewage effluent per week continuously throughout the year.
Approximately 432 inches of effluent have been applied to the area as
of December 31, 1969. The soil at this site is a Morrison sandy loam
rather than Hublersburg clay loam.
The average concentration of constituents in the sewage effluent and
in the percolate water samples collected at various soil depths during
1966 to 1968 are given in Tables A-37 to A-39 in the Appendix. Results
for 1969 are given in Table 134. Average concentrations of constitu-
ents in natural percolating water on the control plots is given in
Table 135.
It is quite apparent that at this year round application of wastewater
the concentration of phosphorus was still being substantially decreased
in 1969 from a mean annual value of 5.532 mg P/l in the applied efflu-
ent to a value of 0.137 in the soil water at a depth of 48 inches.
However average concentration of nitrate-nitrogen in the percolating
water at the 4-foot soil depth was 23.7 mg/1. This is more than twice
.the recommended limit (10 mg/1) for potable water. In comparison,
average nitrate-nitrogen concentration in the control area was only 0.3
mg/1 (Table 135).
A summary of the nitrate data for all the forested areas is given in
Table 136 and shown graphically in Figure 73. It is clear that the
forested areas can handle a 1-inch per week application without having
the mean annual concentration of the 48-inch depth exceed the Public
Health Service limit. However, when 2 inches were applied per week
either in the April-Nov period with red pine on the Hublersburg soil
or year-around with hardwoods on the Morrison soil the NOj-N concentra-
tion at the 48-inch depth rapidly exceeded the Public Health Service
limit. On the other hand, 2 inches of wastewater applied weekly on
the old field area in the April-Nov period did not result in excessive
N03-N values at the 48-inch depth.
The difference between the 2-inch red pine and 2-inch old field areas
on the same soil type probably resides in the difference in the re-
cycling of the nitrogen through the two vegetative covers. In the red
pine relatively less nitrogen is assimilated in the annual growth than
in the herbaceous annuals and perennials in the old field and larger
amounts of readily decomposable organic residues are deposited annually
in the old field. The larger quantities of carbonaceous material in
the old field area may also promote a higher degree of denitrification
in this fine textured soil. The sandiness of the soil on the 2-inch
hardwood area would not be conducive to denitrification of the larger
nitrogen load applied in a year-around irrigation period and the hard-
wood leaf litter although more decomposable than the red pine needle
litter would not be as decomposable as the old field residues.
275
-------
Table 134. Average Concentration in Percolate Samples Collected from Forest Floor Pans and Tension
Lysimeters in the New Gamelands Area Which Received 2" of Effluent Per Ifeek During the
Period 1-1-69 to 12-31-69.
No. of
samples pH MRAS NOj-N Org-N NH4-N Cl P Na K Ca Mg Mn B
Concentration in mg/1
Effluent Quality
Forest Floor Pans
6 inches
12 inches
24 inches
48 inches
30
33
17
22
13
14
7.6 0.41 4.4
7.4 0.22 10.1
7.5 I/ 17.0
7.6 0712 18.5
7.4 I/ 24.4
7.2 0707 23.7
8.1
4.3
1.1
2.2
1.8
1.4
13.8
8.7
1.3
1.8
1.2
1.4
44.5
40.4
43.2
41.3
43.2
49.1
5.532
4.890
0.319
0.415
0.104
0.137
31.7
31.8
31.5
34.7
29.5
39.8
12.4
14.1
13.7
12.6
13.2
17.6
29.9
28.1
37.4
43.6
34.7
38.9
13.6
12.8
20.9
29.3
21.4
22.3
0.10
0.26
0.05
0.03
0.18
0.38
0.27
0.23
0.23
0.24
0.21
0.24
—' Not analyzed.
-------
N>
Table 135. Average Concentration in Percolate Samples Collected from. Forest Floor Pans and Tension
Lysimeters in the Control Plot at the New Gamelands Site During the Period 1-1-69 to
12-31-69.
No. of
sanples pH MBAS NCL-N Org-N NH.-N Cl P Na K Ca Mg Mn B
Concentration in mg/1
Forest Floor Pans
6 inches
12 inches
24 inches
48 inches
27
11
5
4
9
6.9 0.11
7.0 0.07
7.6 0.03
7.3 I/
6.9 0.02
3.6
0.4
0.4
0.1
0.3
3.8
2.9
5.1
3.1
1.2
3.0
1.6
1.3
0.7
0.5
1.0
2.6
1.0
2.4
2.1
0.361
0.031
0.037
0.032
0.059
0.4
1.5
0.8
1.5
1.9
8.3
4.6
6.5
3.9
3.7
15.5
22.4
24.3
35.0
5.8
1.4
11.5
15.3
15.4
3.9
0.62
1.21
0.24
0.06
0.06
0.07
0.04
0.07
0.04
0.04
— Not analyzed.
-------
Table 136. Mean Annual Concentration (mg/1) of Nit rate-Nitrogen in
Suction Lysimeter Samples at Three Depths in Forest Areas
Receiving Various Levels of Wastewater. 1965-1969
Red Pine - Hublersburg Soil
6-Inch Depth 24-Inch Depth 48-Inch Depth
ICCli
1965
1966
1967
1968
1969
Ave
inches per week
012
0.2 1.7 9.2
0.1 1.5 26.8
0.9 6.9 9.6
0.5 18.7 21,8
0.1 17.6 10.5
0.4 9.3 15.6
inches per week
012
0.4 10.7
0.2 0.2 14.6
0.4 5.1 10.6
0.2 6.1 17.6
0.2 9.0 19.6
0.3 4.2 14.6
Hardwood - Hublersburg
6 -Inch Depth 24- Inch Depth
Year
1965
1966
1967
1968
1969
Ave
Year
1965
1966
1967
1968
1969
Ave
inches per week
0 1
0.1 1.0
0.1 3.3
0.4 13.3
0.4 10.9
0.4 6.8
0.3 7.1
Old
6 -Inch Depth
inches per week
0 2
0.1 5.1
0.1 4.3
0.4 4.6
0.0 4.8
0.4 7.3
0.2 5.2
inches per week
0 1
0.2
0.1 2.1
0.4 5.4
0.2 10.0
0.3 4.9
0.3 • 4.5
Field - Hublersburg
24- Inch Depth
inches per week
0 2
0.1 8.4
0.4 7.5
0.4 12.0
0.2 4.9
0.4 8.3
0.3 8.2
inches per week
0 1 2
0.9 2.2 3.9
0.1 2.1 9.3
0.9 1.7 13.8
0.9 2.7 19.9
0.2 4.2 24.2
0.6 2.6 14.0
Soil
48 -Inch Depth
inches per week
0 1
0.0
0.1 0.2
0.3 1.4
0.1 8.0
0.1 7.2
0.2 3.4
Soil
48- inch Depth
inches per week
0 2
0.3 8.0
0.1 5.0
0.3 6.1
0.2 3.7
0.2 2.3
0.2 5.0
278
-------
Table 136. Continued.
Year
Ave
Hardwood - Morrison Soil
24-Inch Depth
inches per week inches per week
0202
6-Inch Depth
0.2
17.2
o.3
21.4
48-Inch Depth
inches per week
0 2
1966
1967
1968
1969
0.2
--
0.1
0.4
12.5
16.9
22.3
17.0
0.5
0.5
0.2
0.1
14.9
20.4
26.0
24.4
0.1
1.4
0.1
0.3
10.6
19.2
25.9
23.7
0.5
19.9
Hardwood - Hublersburg Soil
6-Inch Depth 24-Inch Depth 48-Inch Depth 72-Inch Depth
YG*LT* —~~'- ~ i L —•-• - -•-•' ' -• i f • - *— — —— ••••• •• •" - . .1 A. . i.—
inches per week inches per week inches per week inches per week
0 40 40 40 4
1965
1966
1967
1968
0.1
0.1
0.4
0.4
7
11
8
8
.3
.1
.6
.8
_.
0.1
0.4
0.2
4
9
5
3
.2
.3
.1
.2
.
0.
0.
0.
.
1
3
1
2.
9.
3.
0.
3
1
4
9
5.2
9.5
8.3
8.2
Ave
0.3
9.0 0.2
5-. 5
0.2
3.9
7.8
Further support for the importance of denitrification in decreasing the
inputs of nitrate to the groundwater was obtained in the data from the
Hardwood area on the Hublersburg soil which received four inches of
wastewater, weekly, in the April-Nov period (Table 136). The effluent
was applied during the week in two 2-inch applications separated by a
2- and 3-day interval. In spite of doubling the nitrogen load, the
NC>3-N concentration at 48 inches remained below 10 mg/1, probably
because the larger hydraulic load encouraged more denitrification.
Results for all of the constituents on the 4-inch plot are given for
1965 to 1967 in Tables A-40 to A-42 in the Appendix and for 1968 in
Table 137.
Results for 1968 shown in Table 137 indicate that even at this higher
rate of disposal considerable renovation is achieved. Average concen-
tration of constituents and renovation is almost equivalent to that
obtained at the 1-inch rate of application even after applying almost
648 inches of effluent from 1963 through 1968. Average concentration
279
-------
25
20
o:
UJ
a: 15
UJ
a.
e>
?IO
I
cT
1965 1966
1967 1968
YEAR
1969
Figure 73. Msan Annual Nitrate-Nitrogen Concentration in Suction
Lysimeter Samples at the 48-inch Depth ort Various
Forest Area. 1965-1969
280
-------
Table 137. Average Concentration of Constituents in the Applied Sewage Effluent and in the Percolate
Water Samples Collected from Pan Lysimeters Located in the Hardwood Plot Which Received
4 Inches of Effluent Per Week During the Period April 15 to October 14, 1968.
No. of
samples pH MBAS NOj-N Org-N NH4-N Cl P Na K Ca Mg Mn B
Concentration in mg/liter
Effluent Quality 27 7.70.59 5.1 6.4 13.2 46.4 8.455 40.2 18.6 26.4 13.3 0.12 0.37
Soil Depth-inches
6
12
24
t-o 35
~ 48 19 7.4 0.12 0.9 0.9 0.5 53.1 0.050 54.9 3.2 7.1 6.2 0.04 0.12
51
45
37
31
7.4 0.29 8.8
7.4 0.20 6.3
7.1 0.09 3.2
7.1 0.11 4.4
3.0
3.2
0.8
0.5
9.1
3.5
1.0
1.1
46.3
55.6
66.9
77.3
6.077
2.821
0.063
0.050
41.0
39.5
54.6
53.2
13.7
12.9
6.6
5.3
26.1
18.3
10.6
9.5
13.4
12.6
6.8
9.5
0.09
0.07
0.34
0.36
0.29
0.27
0.27
0.28
-------
of MBAS in 1968 at the 4-foot depth was only 0.12 mg/1 in comparison
to 0.09 mg/1 on the plot receiving the one inch rate. Similarly,
phosphorus concentrations in 1968 were only 0.050 mg/1 (99.4 percent
renovation) in comparison to 0.047 mg/1 at the 1-inch per week appli-
cation. Nitrate-nitrogen concentration in 1968 was extremely low 0.9
mg/1 in comparison to 7.2 mg/1 on the plot receiving one inch. The
greater degree of wetness maintained in this area may have triggered
more denitrification losses of nitrate in the deeper layers of this
fine textured soil.
Renovation efficiency of the 4 inch per week forest plots has remained
relatively constant in terms of removing MBAS and phosphorus as shown
by the trends of the average annual concentration (Figures 74 and 75).
The large decrease in MBAS in the effluent from 3 mg/1 in 1963 to less
than 1 mg/1 in 1968 was the result of improved efficiency of sewage
treatment in 1964 and 1965 and of the conversion by the detergent
industry from branched to linear alkyl benzene sulfonates.
Average annual concentrations of nitrate-nitrogen varied widely at the
various soil depths (Figure 76). No distinct trends are evident except
that the average concentration in the percolate has remained less than
10mg.NO,-N per liter.
\
Soil Chemical Characteristics
Soil samples were taken to depths of 3 and 5 feet in the fall of 1963
after cessation of irrigation, in the spring of 1964 prior to initia-
tion of irrigation, and again in the fall of 1965. Mean nutrient
element concentrations at various depths are given in Tables 138 and
139 for the hardwood 1- and 4-inch irrigated plots and control plot.
Soil samples were analyzed for the same constituents as was the efflu-
ent to determine if significant concentrations of nutrients were
accumulating in the irrigated plots. If so, at what depths were
elements concentrating? Was any one group of constituents replacing
another group on the soil exchange sites? What was the effect of
natural precipitation on nutrient redistribution? What was the change
in nutrient status with time?
Total nitrogen was analyzed by the standard Kjeldahl method with modi-
fication to include nitrates. The detergent constituent, MBAS, was
extracted from the soil with benzene and methanol and analyzed by the
methylene blue color method. Chloride was extracted with 0.05N NfyNOj
and titrated with an Aminco - Cotlove titrator. Phosphorus was ex-
tracted with O.Q3N NH4F in 0.025N HCL using the Bray procedure. Boron
and exchangeable cations (K, Ca, Mg, Na, Mn) were extracted with a
1 N MfyAc at pH 7.0. The total extract was evaporated to dryness at
105°C and the residue analyzed with an arc emission spectrometer.
282
-------
3.0
2.5
2.0
1.5
CP
I
CO
<
00
1.0
0.5
\
i
\
\
*
\
Effluent Quol ity
•—» • • 12 inch soil depth
— 24 inch soil depth
48 inch soil depth
«
\
\
i
\
1963
1964
1965
year
1966
1967
1968
Figure 74. Msan Annual MBAS Concentration in Suction Lysimeter
Samples at Three Depths and in the Applied Wastewater
in the Hardwood Area on Hublersburg Soil Which
Received Four Inches of Wastewater Weekly. 1963-1968
283
-------
OO
10
8
o»
E
Effluent Quality
• 12 inch soil depth
24 Inch soil depth
48 inch soil depth
1963
1964
1965
year
1966
1967
868
Figure 75. Msan Annual Phosphorus Concentration in Suction Lysimeter Samples at Three Depths and
in the Applied Wastewater in the Hardwood Area on Hublersburg Soil Which Received Four
Inches of Wastewater Weekly. 1963-1968
-------
to
oo
en
10 .
8 .
o»
IO
. 12 Inch
24 inch
48 inch
1963 1964 1965 1966 1967 1968
year
Figure 76. Mean Annual Nitrate-Nitrogen Concentration in Suction Lysimeter Samples at Three Depths
in the Hardwood Area on Hublersburg Soil Which Has Received Four Inches of Wastewater
Weekly. 1963-1968
-------
Results indicated that there was no significant accumulation in total
nitrogen. MBAS content also was not significantly higher in the
irrigated plots which appears to indicate that degradation and utili-
zation of MBAS by the soil microorganisms is quite rapid. Phosphorus
is readily fixed by the soil so most of it is held in an unavailable
form. As shown in Tables 138 and 139, there was a highly significant
increase of Bray extractable phosphorus in the upper foot of soil on
both irrigated plots. However, phosphorus accumulation is not antici-
pated to be a problem.
Since the effluent is high in chlorides one would expect that chloride
content would be higher on the irrigated plots. Moreover, since
chlorides are not strongly adsorbed by soil colloids, they do not
attenuate in concentration with increasing depth as does the phosphate.
There was no significant difference between the irrigated and control
plots in the amounts of NIfyAc extractable calcium, magnesium, potassium,
manganese, or boron. Although the mean concentrations of calcium and
magnesium are higher on the 4-inch irrigated plot than on the control
plot, the difference is not statistically significant.
There was a significant increase in exchangeable sodium on all irri-
gated plots. Significant accumulations were evident to a depth of 3
feet. The maximum content found was less than 0.5 m.e. per 100 g. in
the upper foot and less than 0.3 m.e. at greater depths. Under the
normal, humid climate of Pennsylvania it is not anticipated that the
accumulation of sodium will be great enough to cause a soil structure
problem.
A comparison of the soil chemical status at the end of irrigation in
1963 with the soil chemical status in the spring of 1964 prior to the
start of irrigation should provide some insight into the extent of
desorption and constituent redistribution by leaching (Table 138). A
total of 11.66 inches of precipitation occurred during the dormant
period and was about average for the area. Averaging the concentration
in the upper foot in the spring of 1964 and comparing it with the upper
foot in the fall of 1963, only the average concentrations of Na and Mn
decreased over the winter. Chloride which one would expect to desorb
most readily was present in larger quantities in the spring.
The soil does not appear to be adsorbing or releasing any particular
cation or group of cations. The ratio of monovalent cations (Na and K)
to divalent cations (Ca and Mg) has remained approximately the same in
the irrigated and control plots.
Mean chemical element concentrations in the soil samples collected in
the other irrigated areas (red pine 1- and 2-inch plots and open area
2-inch plot) and their respective control areas are given in Appendix
Tables A-43 to A-45.
286
-------
Table 138. Mean Concentration of Chemical Elements in the Soil Samples Collected in 1963, 1964,
and 1965 in the Hardwood 1-Inch Treatment and Control Plots.
Is)
00
Depth N
feet %
1963 (Fall)
1.0 0.068
2.0 0.035
3.0 0.026
1964 (Spring)
0.5 0.119
1.0 0.045
2.0 0.041
3.0 0.036
1965 (Fall)
0.5 0.216
1.0 0.071
2.0 0.034
3.0 0.031
4.0 0.024
5.0 0.020
Cl
yg/g
21.3
12.5
11.5
22.3
32.1
9.1
51.4
21.8
11.9
22.6
14.5
20.4
22.4
Dilute
Bray Ext;
P
vg/g
24.08
6.77
4.48
73.36
26.69
11.67
11.99
204.17
130.08
9.38
6.11
3.50
2.52
r, - ,
K
me/lOOg
0.39
0.29
0.45
0.53
0.50
0.47
0.37
0.91
0.62
0.76
0.67
0.82
0.45
Ammonium Acetate Extractable
Ca
me/lOOg
TREATMENT
1.0
0.7
0.8
1.3
0.6
1.2
1.8
4.1
0.8
0.7
0.7
0.7
0.6
Mg
me/lOOg
.
0.3
0.9
1.1
0.6
--1.9
0.9
1.5
1.9
0.4
0.5
1.0
1.2
1.2
Mn
Wg/g
150
68
72
92
90
58
52
17
26
14
17
16
28
B
Na
Extr
MBAS
yg/g me/lOOg yg/g
0.8
0.4
0.6
0.8
0.8
0.4
0.6
0.8
0.6
0.8
0.6
0.6
0.4
0.30
0.22
0.15
0.33
0.16
0.27
0.24
0.47
0.24
0.28
0.23
0.26
0.20
—
—
—
—
—
= __
—
5.2
1.4
1.7
1.0
0.7
0.7
-------
Table 138. Continued.
IS)
CO
00
Depth N
feet
1963
1.0
2.0
3.0
1964
0.5
1.0
2.0
3.0
1965
0.5
1.0
2.0
3.0
4.0
5.0
%
(Fall)
0.134
0.061
0.042
(Spring)
0.239
0.066
0.054
0.039
(Fall)
0.281
0.073
0.026
0.025
0.016
0.016
Cl
wg/g
-
5.7
9.0
7.2
21.8
10.8
12.9
11.5
7.7
7.1
5.4
7.5
17.0
16.3
Dilute
Bray Extr
P
vg/g
88.29
16.24
4.81
42.70
24.41
4.48
1.54
43.35
30.94
11.34
6.43
4.15
3.50
.Ammonium Acetate Extractable
K
me/lOOg
0
0
0
0
0
0
0
0
0
0
0
0
0
.31
.34
.42
.58
.23
.37
.42
.94
.56
.62
.62
.59
.73
Ca
me/lOOg
CONTROL
1.4
1.7
1.6
2.6
0.8
1.2
1.3
4.2
0.6
1.1
1.3
0.9
0.9
Mg
me/10 Og
0.3
1.3
1.8
0.4
0.4
1.2
2.1
0.5
0.3
0.8
1.5
1.2
1.4
Mn
vg/g
208
104
75
334
98
64
44
46
24
15
10
9
11
B
Na
yg/g me/lOOg
0.4
0.2
0.4
0.4
0.4
0.2
0.2
0.8
0.6
0.8
0.6
0.6
0.8
0.19
0.20
0.18
0.21
0.22
0.22
0.26
0.22
0.09
0.16
0.10
0.16
0.18
Extr
MBAS
Ug/g
—
—
—
—
—
—
—
4.5
2.3
3.0
0.8
0.8
0.5
-------
to
oo
Table 139. Mean Concentration of Chemical Elements in the Soil Samples Collected in 1965 in the
Hardwood 4-Inch Treated Plot.
Depth N
feet %
Dilute
RTIV Pirf"r — -
t> L ciy £jA ul — — • —
Cl P K
yg/g vg/g me/lOOg
Ammonium
Ca
me/lOOg m«
Acetate
Mg
J/lOOs
Extractable
Mn
us/e
B Na
ug/e me/lOOg
Extr
MBAS
yg/g
TREATMENT
1965 (Fall)
0.5
1.0
2.0
3.0
4.0
5.0
0.160
0.044
0.033
0.033
0.022
0.016
8.4
2.7
10.0
5.9
20.3
22.5
556.67
251.42
34.53
8.73
12.32
18.53
1.18
0.79
0.82
0.64
0.64
0.61
6.5
1.6
1.2
2.2
2.2
1.9
3.1
1.2
0.9
2.9
2.5
1.9
6
10
9
8
7
9
1.0
0.6
0.8
0.4
0.6
0.6
0.39
0.29
0.36
0.39
0.36
0.27
3.5
1.2
0.5
0.4
0.3
0.5
CONTROL
Control Plot is the same as for the hardwood 1-inch.
-------
Nutrient Composition of Foliage
Foliar samples from the hardwoods, red pines, white spruce, and ground
vegetation in the old-field plot were collected and analyzed to deter-
mine the extent of utilization of the nutrient elements in the sewage
effluent. Results for the analyses of samples collected at the end of
the growing season in 1965, 1966 and 1967 are given in Tables 140 to
142. The nutrient element content in the foliage of the vegetation on
the irrigated plots in 1967 was generally higher in nitrogen, phos-
phorus, magnesium, boron, and sodium and lower in manganese than that
in the vegetation on the control plots. It is therefore obvious that
this higher concentration together with a generally greater growth of
the forest vegetation is at least temporarily contributing to the
renovation of the percolating effluent; however, its ultimate contri-
bution is difficult to estimate because the annual storage of nutrients
in the woody tissue and the extent of recycling of nutrients in the
forest litter are extremely difficult to measure.
Although considerable amounts of nutrients may be taken up by trees
during the growing season, many of these nutrients are redeposited
annually in the leaf and needle litter rather than being hauled away
as in the case of harvested agronomic crops.
Tree Growth Responses
Diameter and height growth measurements were made annually on sample
trees selected at random on each irrigated and control plot. Average
annual diameter growths for the red pine and mixed hardwood plots are
given in Table 143. Results indicated that weekly irrigation of red
pine with 1 and 2 inches of sewage effluent did not significantly
increase diameter growth. In fact, it is quite obvious that the 2-
inch per week application actually caused a significant decrease in
diameter growth.
Average annual diameter growth of the mixed hardwood species was not
affected by the 1-inch per week application on the older stand but was
significantly increased on the younger stands which received 2 or 4
inches per week. Annual increases in diameter growth ranged from 27
to 200 percent.
Results of the height growth measurements in the red pine plots are
given in Table 144. Irrigation with sewage effluents at both rates
produced slight increases in height growth during the first 2 years.
This slight increase in height growth has been maintained in the plot
receiving 1 inch per week, however, during the last 4 years height
growth on the plot receiving 2 inches per week has been significantly
reduced. In addition the needles in the upper part of the canopy
were starting to turn yellow. In 1968, high winds following a wet
snowfall completely felled every tree on the 2-inch plot. The plot
290
-------
Table 140. Average Chemical Content of Tree Foliage and Old Field
Ground Vegetation at the End of the 1965 Irrigation
Season.
Plot
Farm WoocHot Area
Hardwood 1-inch
Irrigated
Control
Fed Pine 1-inch
Irrigated
Control
Red Pine 2 -inch
Irrigated
Control
Old Field 2 -inch
Irrigated
Control
Gameland Area Hardwood
Irrigated
Control
Gameland Area Hardwood
Irrigated
Control
N
P
K
Ca
Mg
Percent of dry weight
2.49
2.62
1.58
1.23
1.98
1.26
2.66
1.29
2 -inch
3.05
2.18
4- inch
3.04
2.31
.167
.156
.152
.160
.142
.162
.366
.133
.218
.146
.244
.152
1.04
1.13
0.73
0.81
0.66
0.86
2.25
1.52
1.22
1.08
1.22
1.24
0.83
0.90
0.26
0.22
0.24
0.21
1.35
1.12
0.83
0.62
0.73
0.83
.140
.114
.085
.094
.087
.078
.396
.152
.140
.103
.130
.120
B
ygm/gm
98
48
27
22
29
21
55
42
111
47
106
48
291
-------
Table 141. Average Chemical Content of Tree Foliage and Old Field
Ground Vegetation at the End of the 1966 Irrigation
Season.
Plot
N
P
Percent
Farm Woodlot Area
Hardwood 1-inch
Irrigated
Control
Red Pine 1-inch
Irrigated
Control
Red Pine 2 -inch
Irrigated
Control
Old Field 2- inch
Irrigated
Control
White Spruce 2 -inch
Irrigated
Control
Gameland Area
Hardwood 2 -inch
Irrigated
Control
Hardwood 4 -inch
Irrigated
Control
2.
2.
1.
1.
2.
1.
2.
1.
2.
1.
2.
3.
3.
3.
41
29
75
17
18
34
74
45
38
56
75
23
03
23
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
137
130
180
166
•
142
169
344
158
247
163
179
141
186
141
K
Ca
Wfe
of dry weight
0.
1.
0.
0.
0.
0.
2.
1.
0.
0.
1.
1.
1.
1.
95
06
59
57
58
63
10
37
55
56
07
20
11
20
0.71
0.75
0.25
0.19
0.25
0.19
1.19
1.06
0.51
0.55
0.61
0.80
0.53
0.80
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
157
125
084
082
091
070
426
165
086
084
185
129
212
129
B
ygra/gm
104
52
33
20
29
22
62
34
38
17
93
57
102
57
Na
Vigm/gra
14
12
84
9
83
16
395
28
56
6
12
12
12
12
292
-------
Table 142. Average Chemical Content of Tree Foliage and Old-Field Ground Vegetation at the End of
the 1967 Irrigation Season.
Plot N
Farm Woodlot Area
Hardwood 1-inch
Irrigated 2 . 45
Control 2.20
Red Pine 1-inch
§ Irrigated 1.62
Control 1.15
Red Pine 2 -inch
Irrigated 2.17
Control 1.33
Old-Field
Vegetation 2 -inch
Irrigated 3.28
Control 1.30
P
Percent
0.22
0.18
0.17
0.16
0.13
0.15
0.45
0.16
K
Ca
Mg
of dry weight
0.86
0.87
0.58
0.53
0.52
0.61
2.34
1.19
1.00
0.99
0.19
0.29
0.26
0.24
1.23
1.09
0.14
0.08
0.09
0.09
0.10
0.08
0.44
0.13
Mn
1500
1845
942
1103
947
925
235
642
Fe
88
80
41
53
58
54
379
400
Cu
8
7
4
4
4
3
19
13
B
Vg/g
81
49
28
19
33
23
39
35
«
68
66
142
496
97
394
825
958
Zn
26
27
33
45
32
40
94
95
Na
15
16
44
8
114
11
473
28
-------
Table 142. Continued.
to
to
Plot N
White Spruce 2 -inch
Irrigated 2.19
Control 1.48
Hardwoods 2-inchi/
Irrigated 2.97
Control 2.20
P
Percent
0.59
0.19
0.29
0.18
K
Ca
Mg
of dry weight
0.67
0.71
0.93
1.13
0.84
0.93
0.77
1.01
0.12
0.13
0.19
0.09
Mn
517
834
1830
2725
Fe
90
57
81
83
Cu
6
5
7
8
B
vg/g
38
26
117
65
Al
87
100
50
80
Zn Na
35 117
95 10
33 13
25 16
-------
Table 143. Average Annual Diameter Growth for Period 1964 to 1969.
tsi
VO
cn
Plot
Red pine 1-inch
Red pine control
Red pine 2 -inch
Red pine control
Mixed hardwood 1-inch
Mixed hardwood control
Mixed hardwood 2 -inch
Mixed hardwood control
Mixed hardwood 4 -inch
Mixed hardwood control
1964
inches
0.10
0.10
0.07
0.13
0.16
0.15
1965
inches
0.08
0.09
0.05
0.11
0.18
0.15
0.22
0.13
1966
inches
0.07
0.12
0.07
0.12
0.16
0.16-
0.15
0.05
0.19
0.15
1967
inches
0.13
0.14
0.09
0.15
0.13
0.14
0.29
0.12
0.23
0.15
1968
inches
0.07
0.08
0.04
0.09
0.12
0.17
0.24
0.11
0.14-/
0.13
1969
inches
0.05
0.08
0.08
0.16
0.18
0.23
0.14
0.25i/
0.20
Average
diameter
growth
inches
0.08
0.10
0.06
0.11
0.15
0.16
0.23
0.10
0.21
0.15
I/
Winter irrigation only.
-------
Table 144. Average Annual Teiminal Height Growth in the Red Pine
Plots During the Period 1963 to 1968.
Plot
Red pine 1-inch
Red pine control
Red pine 2 -inch
Red pine control
1963
feet
1.2
1.2
1.5
1.4
1964
feet
2.1
1.6
2.2
2.0
1965
feet
2.0
1.3
1.6
1.9
1966
feet
1.7
1.4
1.4
1.8
1967
feet
1.8
1.6
1.5
1.6
1968
feet
1.7
1.5
1.3
1.6
Average
height
growth
feet
1.7
1.4
1.6
1.7
Table 145. Average Annual Height Growth of White Spruce
Plot
White Spruce 2 -inch
Control
Percent Increase
'1963
feet
0.97
0.83
17
1964
feet
2.19
1.35
62
1965
feet
1.74
0.58
200
1966
feet
2.04
0.75
172
1967
feet
2.18
0.88
148
1968
feet
2.28
1.43
60
1969
feet
2.10
1.46
44
Average
height
growth
feet
1.92
0.92
108
was cleared in 1969 and replanted with white pine seedlings which have
been shown to be more adaptable to irrigation with sewage effluent on
this fine textured soil.
Height growth response of the white spruce saplings which received 2
inches of effluent per week was significantly increased. During the
7 years of irrigation average annual height growth of the irrigated
trees was 1.92 feet in comparison to 0.92 feet on the control plot-
(Table 145). Average annual height growth was significantly increased
by 62 to 200 percent. At the start of the study, the height of the
white spruce ranged from 3 to 8 feet. At the end of the growing season
in 1969, the average height of the trees on the control plot was 6 feet
and on the irrigated plot 18 feet.
296
-------
Herbaceous Vegetation Growth Responses
Transect plots were also established in the old field spruce stand to
measure growth responses of the ground vegetation and to determine
the effect of sewage effluent on site productivity. Average annual
dry matter production on the irrigated plot was 5,532 pounds per acre
in comparison to 1,650 pounds per acre on the control plot (Table 146)
This represents an average annual increase of 235 percent. Annual
increases ranged from approximately 100 to 350 percent. Average
height of the predominant plant species was 4.4 feet on the irrigated
plot in comparison to 1.3 feet on the control plot. In addition,
approximately 10 percent of the control plot was barren of vegetation;
whereas, the irrigated plot had a complete dense vegetation cover.
Table 146. Growth Response of Ground Vegetation in the Open White
Spruce Plots, Expressed in Terms of Dry Matter Production.
Irrigated Control
Year Plot Plot
Ibs/acre Ibs/acre
1963
1964
1965
1966
1967
1968
3,381
7,607
5,672
6,417
4,075
6,044
1,470
1,763
1,675
1,435
2,010
1,550
Average 5,532 1,650
Tree Seedling Survival and Growth Study
Eight tree species were also planted in an open field area in 1965 to
determine which species might be best suited for sites to be used as
disposal areas for sewage effluent. One- and two-year-old seedlings
of European larch (Larix decidua), Japanese larch (Larix leptolepis),
white pine (Pinus strobus), red pine, white spruce, pitch pine (Pinus
rigida), Austrian pine (Pinus nigra), and Norway spruce (Picea abies)
were planted in a randomized block design with three blocks irrigated
with 2 inches of effluent per week and three blocks maintained as a
control. Each block contained 10 trees of each species or a total of
80 trees per block. First-year survival (1965) over all species on
the irrigated plot was 88 percent and on the control plot, 52 percent
(Table 147). Continued irrigation with wastewater resulted in average
297
-------
Table 147. Survival of Planted Tree Seedlings - 1965-1969.
Year
Species
1965 1966
A-i/ B A B
Survival
1967
A B
- percent
1969
A B
White pine
Red pine
Norway spruce
White spruce
Pitch pine
Austrian pine
European larch
Japanese larch
100
100
97
97
93
90
80
47
87
93
46
33
80
47
23
7
80
77
77
63
33
30
30
20
60
77
13
20
50
47
10
6
70
53
57
43
10
13
23
17
50
53
13
13
20
40
6
0
70
43
47
33
3
13
23
17
20
23
7
3
3
17
0
0
Average
88
52
51 35
36 24
31
I/
A = irrigated; B = control
survivals of 31 percent and 9 percent in 1969 on the irrigated and
control'areas.
The total height growth of surviving seedlings at the end of the
growing season in 1969 is shown in Table 148. Results indicate that
European and Japanese larch and white pine had the greatest growth
response to sewage effluent irrigation.
298
-------
Table 148. Average Total Height Growth of Surviving Seedlings in the
First Year, 1965, and in 1969.
Total Height Growth - feet
sPecies Irrigated Control
1965 1969 1965 1969
European larch
Japanese larch
White pine
Red pine
White spruce
Pitch pine
Austrian pine
Norway spruce
0.38
0.46
0,28
0.28
0..20
0.24
0.20
0.22
6.8
6.4
5.1
3.0
2.9
2.9
2.7
2.4
0.04
0.03
0.18
0.15
0.15
0.10
0.17
0.25
!/
I/
271
1.6
- 2.2
1.0
1.9
1.4
- No trees survived in 1969-
299
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SECTION VIII
GEOHYDROLOGY
MONITORING RESULTS
Data obtained from chemical analyses of soil-water collected from
depths of 6 to 26 feet below landsurface are considered here together
with data from on and offsite deep monitoring wells at depths of 100
to_370 feet. Chemical data are presented for only selected monitoring
points to show the ranges in conditions encountered. Data showing the
best and worst conditions experienced on site are given along with more
representative data.
Procedures
Considerable variability in chemical quality may result due to daily,
weekly and monthly variations in precipitation, farming practice, and
other factors.
Some scatter in water quality values also may be considered as aberrant
values because there is reason to believe that data from contaminated
samples may have been included in the mass of data obtained. Examples
may be isolated from the data where an abnormally high concentration of
a particular constituent was recorded which is preceded and followed by
a sequence of much lower values. This casts doubt on the occasional,
isolated aberrant values particularly for waste constituents such as
phosphorus which does not have the mobility implied by the data. In
some samples, particularly from shallow sand point wells, suspended
sediment which was not obviously present interfered with the chemical
analysis procedure for phosphorus. Such aberrant values usually fell
at the upper end of the range.
All data were included in the quality frequency plotting discussed
below. The aberrant phosphorus values were removed prior to computing
the analysis of variance of the yearly means and applying the Duncans
multiple range test of the difference between annual means.
In the frequency plotting the quality data are tabulated in descending
order of magnitude and the equation Pm = m/(Nw+l) 100 (95) is used to
assign relative frequencies of samples whose concentrations are equal
to or greater than the concentration of a particular sample. In this
equation m is the order number of the sample concentration value, Nw is
the total number of -samples and Pm is the percent of samples whose con-
centrations are equal to or greater than the concentration of sample
with order number m. In plotting the concentration values against Pm
on a logarithmic probability scale it is assumed that the observations
are a random sample from a log normally distributed population. If a
straight line is fitted to the array of values in such a plot the slope
301
-------
will be steep if the range of concentrations is wide and flat if the
range is narrow. For lines of equal slope, the higher the position
of the line the greater is the median concentration. The time sequence
of sampling is ignored in the frequency displays but the effects of
time may be considered in a general way by comparing the arrays of data
grouped for one time period with that of another time period. Some
three and four year displays are given for several off-site and on-site
wells. The statistical significance of the displacement of the arrays
was not evaluated but an analysis of variance procedure and Duncans
Multiple Range test was used to evaluate the significance of the differ-
ences of the annual means of twelve of the monitoring wells (Tables 149 -
151).
Agronomy-Forestry Area
Well Characteristics. Figure 2;. shows the proximity of monitoring
wells to the Agronomy-Forestry Site. F-l, 2, 3, 4, and 5 and UN-14
are the principal qnsite wells. F-l, 2, and 5 are closest to irriga-
tion plots; F-4, UN-14 and F-3 are further away. Each well site was
selected to provide control under a set of specific conditions. UN-14,
for example, is a university water supply well with a potential capa-
city of in excess of 500 gpm. It routinely produced from 150 to 250 gpm
since 1964. This well intercepts a considerable portion of the re-
claimed effluent which is diverted to the nearby University well field
shown in Figure 2.
It has been shown by Parizek (96), Siddiqui and Parizek (97) and
Parizek ( 98) that valley bottoms such as Big Hollow tend to favor
permeability development within carbonate rocks for a variety of reasons
that include an interaction of structure, rock type, surface and ground-
water flow. Parizek ( 98 ) showed five basic mechanisms that are
involved in developing anisotropic permeability beneath the valley
environment that have a bearing on the location of monitoring well UN-14.
Big Hollow is a dry underdrained karst valley all but for brief periods
of the year when perched runoff may occupy segments of the valley.
Water enters the surface by diffuse infiltration along somewhat perme-
able flood plain deposits, and within small sinkholes. The water table
underlay this valley by 15 to 35 feet or more when the first University
supply wells were drilled in Big Hollow. The course of Big Hollow is
in part controlled by the more soluble Stonehenge Limestone which now
serves as the eastern valley wall, by intersecting zones of fracture
concentration which help to localize the center of the valley and its
dry tributaries, and which add greatly to bedrock permeability, and
locally by systematic joint sets and fault zones. These structural and
stratigraphic factors have combined to localize permeability develop-
ment along with concentrated solution of dolomite and limestone within
the valley environment ( 98).
302
-------
Aside from the higher productivity of wells located within this
valley compared with wells drilled into similar rock on adjacent up-
lands, the increased permeability along the valley bottom of Big
Hollow is revealed by the water table maps shown in Figures 4 and
5. Water table contour lines extend up and down the valley in
response to pumping in the University well field following more perme-
able strata. This has produced an elongate cone of depression typical
of rocks with anistropic permeability characteristics. These water
table lows mark groundwater drains or avenues of increased groundwater
flow which may extend for a mile or more up and down the valley. A
1969 water table contour map subsequent to the 1965 map shown in
Figure 5 shows this more dramatically. The map had added control
points to the southwest that helped to better define this relation-
ship but is not included here because few control points were available
at the irrigation sites.
Well UN-14, obtains its water by lateral flow from groundwater mounds
located on either side of the valley walls of Big Hollow including
flow from the Agronomy-Forestry irrigation site as well as flow up
and down Big Hollow. Water quality data for UN-14, therefore, repre-
sents a blend of water reflecting diverse land uses in addition to
effluent disposal. These include occasional runoff from University
barnyards during periods of rapid snow melt and rainfall, use of road
salt to control snow and ice along Fox Hollow Road to the southwest
of the irrigation area, farming and grazing in fields adjacent to UN-
14, manure disposal in fields immediately east and south of UN-14 and
routine liquid sludge disposal in a sinkhole-foundation excavation
located between F-4 and F-6 in Big Hollow. Sludge disposal at that
site was terminated in 1964 but residual effects are to be expected.
A zone of fracture concentration extends from immediately adjacent to
UN-14 back to the region of F-l where reed canarygrass and red pine
plantations were irrigated. This zone of fracture concentration is an
avenue of high permeability as revealed by the favorable yield of UN-
14 drilled near to the zone, and evidence of well developed solution
features observed in the field along the zone of fracture concentra-
tion.
F-l is not on a zone of fracture concentration, but was located on a
groundwater high, which dissipated somewhat during drought years,
1962-1967, in response to heavy pumping in the University well field.
It intercepted water that was being diverted to the well field until
it failed for mechanical reasons early in 1970.
F-2 is on the zone of fracture concentration on which UN-14 was
drilled. It was centrally located in the irrigation plots until 1969
when the New Red Pine irrigation ceased. Severe flowing sand problems,
and falling water levels reduced its use and eventually eliminated
this well from the monitoring program. Because of its small diameter
303
-------
(3 inches) and extensive casing already set, this well could not be
deepened and maintained as a monitoring well.
F-3 is on a zone of fracture concentration in sandy dolomite and in
a valley-bottom tributary to Big Hollow. This setting favors high
permeability development within the rocks underlying the valley for
the reasons stated above. The area receives surface runoff from
adjacent areas during the spring snow melt. The well is located
where residual soils have been thinned by erosion. Dolomite is
exposed at isolated outcrops along the valley walls. F-3 is located
between the irrigated area and nearby private wells located to the
northeast (TVells 30 and 40, Fig. 2 ).
F-4 is down gradient in the direction of groundwater flow from the
2-inch red pine disposal area, and more remote from a zone of fracture
concentration. Groundwater moves beyond F-4 to avenues of high perme-
ability below Big Hollow and then up valley to the University well
field.
F-5 is at the intersection of two zones of fracture concentration
which divert water from the reed canarygrass plots, red pine planta-
tions and abandoned field irrigation plots. The well is immediately
adjacent to the reed canarygrass irrigation area which receives 2-
inches of effluent on a year around basis. It intercepts water moving
toward UN-14 and other wells in the University well field along zones
of fracture concentration and recharge water derived from spring runoff.
Runoff derived from the reed canarygrass area moves by overland flow
past F-5 for at least 100 to 500 feet to the southeast before completely
infiltrating into the soil within a wood lot. This condition occurs
about two or three days out of each year on the average.
Water Quality. It may be seen from Figure 77 , that the chloride
concentration in UN-14 ranged from .09 to 2.5 ppm in 1966, less than
.01 to 4.6 ppm in 1967, and from less than .01 to 7.2 ppm in 1968.
Median values increased from .55 to 1.0 to 3.2 ppm consecutively for
these same years. The comparatively high chloride concentrations
observed for 1968 compared with the two previous years is attributed
in part from other land uses discussed earlier. This suggests that
nearly five years were required before reclaimed effluent migrated
from the Agronomy-Forestry plots in sufficient volume to be detected
on the assumption that the reclaimed effluent was an important if not
a principal source of chloride in UN-14. This delay is reasonable in
view of the fact that only about 12 acres were irrigated during the
growing season of 1963, approximately 33 acres during the growing
season of 1964 through 1971 and that winter irrigation was not ini-
tiated in the reed canarygrass area until 1965. More than one year,
for example, was required to cause a buildup in chlorides in FM-18
which is a 26 foot deep screen well completed in perched groundwater
in residual soil. This shows that chlorides moved slowly through the
304
-------
0.01
12 5 10 20
80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 77. Percent of UN-14 Deep Well Samples with Chloride
Concentrations Equalling or Exceeding Stated Values.
305
-------
clay rich residual soil under the soil moisture regime and irrigation
schedule experienced the first year.
Alternately, with a return to near normal precipitation in 1967 and
normal or above normal precipitation since 1967, the chloride increases
noted in UN-14 might be attributed mostly to increased runoff from
roads and fields adjacent to UN-14 and the various sources of chloride
associated with the use of road salt, leaching of manures applied to
fields on two sides of UN-14, and greater runoff into Big Hollow from
somewhat distant University bams and new service buildings and park-
ing lots.
Nitrate-nitrogen also showed increases in UN-14 in 1967 and 1968 (Fig.
78). Nitrate-nitrogen showed a range of 1.4 to 2.3 ppm and a median
of 1.7 ppm in 1966, 1.4 to 4.9 and a median of 2.6 ppm in 1968, 1.8
to 5.6 and a median of 3.0 ppm in 1968. The 1967 and 1968 plots are
very similar and may reflect increased rainfall in 1967 that may have
flushed nitrate-nitrogen from nearby agricultural lands as well as the
eventual arrival of reclaimed effluent from the nearby irrigation site.
The apparent ABS values in Figure 79 are not significantly different
from background values and are substantially below the recommended
limit for potable water.
The UN-14 phosphorus values have not changed significantly and fluctuate
around a median value of about 0.02mg P/l. (Fig. 80 )
F-3 shows no significant changes in phosphorus, ABS, or N03-N for the
period 1965-1968. The well is stratigraphically located in the direc-
tion of groundwater flow to points of natural discharge along Spring
Creek (Fig. 2 and 5 ) and is between the irrigated areas and nearby
private wells. Results are important because they show that after 6
years of irrigation, groundwater quality 350 feet beyond the outer
fringe of irrigation remained similar to that of background water
quality. Chloride increased slightly by 1968 but still remained with-
in the background range.
Phosphorus values equalled or exceeded by 80% of the values ranged
from .002 and .003 ppm for the years 1965, 1966, 1967 and 1968 (Fig.
81). The median (50%) values were less than .02 ppm and the values
equalled or exceeded by 201 of the values ranged between .02 and .03
ppm for the four years. These are within the background range for
groundwater essentially unaffected by man's activities.
The ABS median values for F-3 (Fig. 82 ) ranged from .02 to .04 ppm.
This range is within the variation associated with determination of
apparent ABS by the methylene blue method.
N03-N for F-3 remained at background levels for the four years
considered (1965-68) (Fig. 83 ). These values are typical of ground-
water in the local carbonate aquifers that are little influenced by
306
-------
100
CD
CL
CO
Q_
CO
CD
10
n r
! i—i—i—i
UN-14
I I
I 2 5 10 20 50 80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 78. Percent of UN-14 Deep Well Sanples with N03-N
Concentrations Equalling or Exceeding Stated Values.
307
-------
I 2 5 10 20 50 80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 79. Percent of UN-14 Deep Well Sanpl.es with ABS Concentrations
Equalling or Exceeding State Values.
308
-------
o>
o
Q_
to
Q.
in
o
0.001
0.01
12 5 10 20
80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 80, Percent of UN-14 Deep Well Samples with P Concentrations
Equalling or Exceeding Stated Values.
309
-------
I I—I
I 1—I—I—I I
II I I I I I I I I I I V I
0.001
12 5 10 20
50
80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 81. Percent of F-3 Deep Well Samples with P Concentrations
Equalling or Exceeding Stated Values.
310
-------
0.001
12 5 10 20
80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 82. Percent of JF-3 Deep Well Sanples with ABS Concentrations
Equalling or Exceeding Stated Values.
311
-------
to
CO
o>
I—I I 1 1—I—I—I—I—I—I 1
F-3
0.001
12 5 10 20
BO 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 83. Percent of E-3; Deep Well Samples with NC^-N Concentrations
Equaling or Exceeding Stated Values.
312
-------
roan's activities. Concentrations equalled or exceeded by 801 of the
values ranged from a low of 0.04 in 1965 to a high of 0.18 ppm in
1966. The median values ranged from a low of 0.4 ppm in 1965 to 0.52
in 1966. The values equalled or exceeded by 20% of the values ranged
from 0.80 to 1.0 ppm.
Chloride values equalled or exceeded by 801 of the values were less
than .02 ppm for 1965, 1966, and 1967, and rose to .35 ppm by 1968
(Fig. 84). Median values were 0.14 ppm in 1965, 0.35 in 1966, 0.30
ppm in 1967 and 1.5 ppm in 1968. Chloride values equalled or exceeded
by 20% of the values were 0.55 in 1965, 0.85 in 1966, 0.75 in 1967 and
3.0 ppm in 1968.
At best these reflect minor changes in quality and the concentrations
are far below 250 mg Cl/1, the U. S. Public Health Service recommended
limit for potable water.
Monitoring well F-4 provided water samples on a regular basis until it
went dry in 1968. Chloride concentrations increased in 1967 over
values observed in 1964-66 and is an indication that reclaimed efflu-
ent must have migrated to this point nearly five years after irrigation
had started. Groundwater flow from the vicinity of part of the irri-
gated areas was toward F-4 and Big Hollow prior to the start of
irrigation. A groundwater mound beneath the Agronomy-Forestry area
continued to favor flow in this direction after irrigation began. The
recharge area for this mound is partly wooded and partly under agri-
cultural development. However, chloride increases must reflect recharge
of reclaimed effluent because no other special changes were noted in
the land use in the area that could account for the increases in
chlorides noted.
The chloride values for F-4 equalled or exceeded by 80% of the values
were between 0.01 and 0.02, 1964 through 1966, and increased to 0.06
ppm in 1967 (Fig. 85). The median values were around 0.05 in 1964,
.02 in 1965, 0.22 in 1966 and increased to 1.2 ppm in 1967. The
values equalled or exceeded by 20% of the values were 0.6 ppm in 1964,
0.14 in 1965, 0.47 in 1966 and 2.8 ppm in 1967. These values are of
no consequence for drinking water quality.
N03-N values for F-4 were higher in 1964 than 1965 and 1966 and
slightly higher than in 1967 (Fig. 86).
The value equalled or exceeded by 80% of the NOvN values for F-4 was
0.32 ppm in 1964, less than 0.04 in 1965 and 1966 and 0.22 ppm in
1967. The median values were 0.52 in 1964, less than 0.01 in 1965 and
1966, and 0.35 in 1967. The N03-N value equalled or exceeded by 20%
of the values was 0.8 in 1964, 0.3 in 1965, 0.2 in 1966, and back to
0.6 ppm in 1967. None of the values are much above background levels
for typical groundwaters in the region.
313
-------
0.001
80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 84'. Percent of F-3 Deep Well Samples with Chloride
Concentrations Equalling or Exceeding Stated Values.
314
-------
a.
to
OS
-D
w.
_0
o
I I I I I—I—I—I—I—I—I 1—I
O.I
0.01
12 5 10 30
80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 85. Percent of F-4 Deep.Well Sauries with Chloride
Concentrations Equalling or Exceeding Stated Values,
315
-------
I—I 1—I 1—I—I—I—I—I—I 1 I
0.001
I 2 5 10 20 50 80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 86. Percent of F-4 Deep. Well Samples with
Equalling or Exceeding Stated Values.
-N Concentrations
316
-------
ABS values for F-4 do not exceed background levels (Fig. 87). Median
values cluster around .03 ppm or less.
Phosphorus values in F-4 also remained at background levels (Fig. 88).
The median values were less than 0.01 ppm in 1964 and 1965, and less
than .02 in 1966 and 1967. The value equalled or exceeded by 20% of
the values was less than 0.03 ppm in 1964 and 1965, and less than 0.05
ppm in 1966 and 1967.
Chemical data from monitoring well F-5 shows a pattern somewhat similar
to UN-14. This well is closest to the Agronomy-Forestry irrigation
site and should reflect the quality of reclaimed effluent with only
limited dilution. It also is located in the direction of concentrated
groundwater flow from irrigated areas to UN-14.
Chloride increased by 1966 and 1967 over 1965 levels followed by a
further increase in 1968 (Fig. 89). The well was not available as a
monitoring point prior to 1965 but 1965 chloride values are similar to
those obtained from other wells at control sites. Reclaimed effluent
must have reached F-5 by 1966 following the expansion of the project in
1965 to include the nearby reed canarygrass and new red pine disposal
sites.
*
The median chloride value in F-5 was 0.12 ppm in 1965, 1.1 in 1966,
0.62 in 1967 and 7.0 ppm in 1968 (Fig. 89). The value equalled or
exceeded by 20% of the values never exceeded 1.5 ppm during 1965, 1966
and 1967 but increased to 8.1 ppm in 1968.
Unlike the chloride values, the N03-N values in F-5 remained at back-
ground levels (Fig. 90). The value equalled or exceeded by 80% of the
values was approximately 0.35 ppm for 1965 and 1968. The median values
for these same two years was about 0.55 ppm and the value equalled or
exceeded by 20 percent of the values was approximately 0.80 ppm. These
results are significant in view of the proximity of F-5 to the irriga-
tion sites and its location on a fracture trace intersection which
should tend to channel groundwater flow to UN-14 and other production
wells in the University well field.
Phosphorus and ABS data for F-5 also are in the background range (Fig.
91 and 92). The median values all were below 0.05 ppm of P and 0.07
ppm of ABS.
Because of the position of F-5 on a groundwater mound maintained by
recharge from reclaimed effluent (Figs. 4 and 5) and with no other
land uses that could account for the chloride values observed in F-5,
it must be concluded that changes in chloride noted are related to
reclaimed effluent. A similar statement with the same degree of con-
fidence cannot be made for UN-14, and F-4. These monitoring points
can show chloride and nitrate changes derived from adjacent land uses
which cannot be separated from a possible wastewater irrigation source.
317
-------
0.
c.
o
CD
Q_
CO
CO
QQ
-------
CD
Q_
(ft
O
Q_
in
v_
O
Q.
O
Q_
i i i i i i i
0.001
12 5 10 20
80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 88. Percent of F-4 Deep Well Saraples with P Concentrations
Equalling or Exceeding Stated Values.
319
-------
0.001
12 5 10 20
80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 89. Percent of F-5'Deep Well Samples with Chloride
Concentrations Equalling or Exceeding Stated Values,
320
-------
0.001
12 5 10 20
80 90 95
Percent of Samples VWh a Concentration
Equaling or Exceeding the Stated Value
Figure 90. Percent of F-5 Deep Well Sanples with N03-N Concentrations
Equalling or Exceeding Stated Values.
321
-------
0.001
12 5 10 20
80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 91. Percent of F- 5 Deep Well Samples with P Concentrations
Equalling or Exceeding Stated Values.
322
-------
CO
a
Q_
CO
m
0.001
0.01
I 2 5 10 20 50 80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 92. Percent of P- 5: Deep Well Samples with ABS Concentrations
Equalling or Exceeding Stated Values.
323
-------
Monitoring well F-l shows lower chloride values than F-5. Both wells
are within a few feet of irrigated areas. However, F-l is closest to
Agronomic test plots that were irrigated only during April through
November beginning in 1963. F-5 is immediately adjacent to the reed
canarygrass plot that received 2 inches of effluent per week year-
round starting in July, 1964. Two zones of fracture concentration
channel reclaimed effluent to F-5 whereas F-l was drilled within a
block of dolomite and sandy dolomite strata bounded by more distant
zones of fracture concentration. Hence F-l should yield water of
lower chloride content because the site receives less irrigation on
an annual basis and dilution should occur during winter months.
The analysis of variance of the mean annual concentration of phosphorus
in the UN wells showed a significant year effect only for UN-14 but
only at the 10% level of significance and even then the last year,
1969, was not significantly different from the first year, 1962, the
pre-test year. (Table 149)
With the F wells only in the case of F-l was the year effect on mean
annual phosphorus concentration significant (P = 0.01) but again the
last year (1969) was not significantly different from the first year
(1963). (Table 149)
The year effect on mean annual concentration of phosphorus was non-
significant for any of the private wells (W-wells). (Table 149)
With respect to nitrate-nitrogen there was a highly significant year
effect with two of the three UN wells (UN-14 and UN-24). These two
wells happened to be closest to the effluent irrigated Agronomy-
Forestry Area but are also located in a sandier soil area which is
more intensively fanned than where the third well (UN-17) is located.
The higher rainfall since 1967 may be pushing more nitrates out of
the sandy soils surrounding UN-14 and UN-24. Of these two wells only
in the case of UN-14 was the nitrate level significantly greater in
the last two years, 1968 and 1969, than in the first two years, 1962
and 1963. (Table 150)
In the case of the F-wells only the F-l well showed a highly signifi-
cant year effect on nitrate concentration and even then the change in
concentration cannot be attributed to effluent irrigation since the
highest value occurred in the first year, 1963. (Table 150)
In the W-wells the year effect on nitrate concentration was significant
(P = 0.01) in three of the four wells but there was no consistent time
pattern which might be ascribed to effluent irrigation. (Table 150)
Although the year effect on mean annual chloride concentration was
highly significant for the three UN wells, the four W-wells and two
of the three F-wells the time pattern was not always consistent with
324
-------
continuing effluent irrigation. For example with the UN wells the
chloride concentration in 1969 was not significantly different from
the value in the first year of record. The same was true for F-3,
W-3, W-5 and W-30. In the other two wells F-5 and W-7 although
chloride concentration was greater in the last year than in the first
year of record, the lowest concentration did not occur in the first
year in W-7 and the highest concentration did not occur in the last
year of record in F-5. (Table 151)
325
-------
Table 149. Phosphorus in Monitoring Wells.
to
Well No.
UN- 14
UN-17
UN-24
F-l
F-3
F-5
G-3
G-10
W-3
W-5
W-7
W-30
Distance^-' 1962
feet
1300
3300
2200
100
1200
200
0
500
5700
5300
2600
5300
O.OlOab^/
0.009
0.010
--
--
--
0.018
--
0.010
0.011
0.005
0.007
Year
1963 1964 1965 1966
Mean annual concentration •
O.OOSa
0.004
0.019
0.020ab
--
—
—
--
0.009
0.011
0.005
0.011
0.002a
0.008
0.016
0.009ab
--
--
--
--
0.019
0.007
0.006
0.004
0.019ab
0.018
0.020
0.053c
0.009
0.042
0.006
--
0.021
0.016
0.023
0.008
O.OlSab
0.018
0.036
0.032b
0.016
0.059
--
--
0.022
0.010
0.003
0.005
1967 1968
- mgP/liter
0.021ab
0.028
0.032
O.Ollab
0.015
0.063
0.028
0.034
0.022
0.031
--
0.020
0.019ab
0.042
0.022
O.OOla
0.016
0.027
0.029
0.036
0.037
0.036
--
0.028
2/
1969 Significance-7
0.021b
0.016
0.019
0.016ab
0.017
0.032
0.019
0.027
6.002
0.015
0.022
0.015
t
N.
N.
**
N.
N.
N.
N.
• N.
N.
N.
N.
S.
S.
S.
S.
S.
S.
S.
S.
S.
S.
— Approximate distance from sewage effluent application area.
-/ Significance of year effect: **, (P = 0.01); *, (P = 0.05); t, (P = 0.10); N.S. - not
significant, (P > 0.10).
—' Duncans separation of annual means at P = 0.05. Annual means having a common letter are
not different.
-------
Table 150. Nitrate-N in Monitoring Wells.
N)
-4
Well No.
UN-14
UN-17
UN- 24
F-l
F-3
F-5
G-3
G-10
W-3
W-5
W-7
W-30
Distance^/ 1962
feet
1300
3300
2200
100
1200
200
0
500
5700
5300
2600
5300
1.6ab^
0.6
0.6ab
--
--
--
0.2ab
--
10. Ic
5.3c
1.3ab
1.9
1963
Mean
/1.9a
0.6
0.6ab
1.4c
--
—
--
--
9.2c
S.Obc
1.9b
1.3
Year
1964 1965 1966
annual concentration -
2.3abc
0.5
0.3a
0.7ab
--
--
--
--
4.6ab
4.0abc
1.3ab
1.9
1.4a
0.2
O.Sa
0.4a
0.4
0.4
O.la
--
3.2a
3.0a
0.7a
1.2
1.8a
O.J
1.2b
0.9bc
0.6
0.6
—
—
S.Oab
3.2a
0.6a
1.4
1967 1968 1969 Significance^
mg NO_-N/liter
2.9bc
0.6
I.Ob
0.9bc
0.4
0.4
3.6b
0.9b
7.6bc
3.7ab
--
2.3
3.1c
0.4
0.9ab
O.Sab
0.5
0.8
3.5b
0.3a
10. 2c
4.4abc
--
2.4
4.
0.
1.
0.
0.
0.
2.
0.
7.
5.
-
2.
Od
4
3b
4a
4
3
8b
4a
3abc
7c
-
2
**
N.S.
**
**
N.S.
N.S.
**
*
**
**
**
N.S.
— Approximate distance from sewage effluent application area.
-/ Significance of year effect: **, (P = 0.01); *, (P = 0.05); t, (P = 0.10); N.S. - not
significant, (P > 0.10).
*
— Duncans separation of annual means at P - 0.05. Annual means having a comnon letter are
not different.
-------
Table 151. Chloride in Monitoring Wells.
oo
Well No.
UN- 14
UN-17
UN-24
F-l
F-3
F-5
G-3
G-10
W-3
W-5
W-7
W-30
Distance^ 1962
feet
1300
3300
2200
100
1200
200
0
500
5700
5300
2600
5300
2.3ab^
1.2ab
--
—
--
--
1.8a
__
13. 3c
4.6d
l.Tb
2.4b
Year.
1963 1964 1965 1966
Mean annual concentration •
/ 2. Sab
l.Sab
--
1.1
--
--
~
--
12. Ic
4.8d
1.8b
2.4b
1.2a
O.la
O.la
0.4
__
__
—
--
3.2a
4.0cd
O.la
0.9a
0.6a
O.Oa
0.2a
0.4
0.5a
0.2a
2.5a
--
4.0a
3.3bcd
3.4b
0.7a
0.8a
0.2a
0.8a
0.3
0.4a
l.Oab
--
__
6. lab
0.6a
6.7c
1.2ab
1967
• mg Cl"
1.3a
0.4a
l.Tb
0.4"
l.Oa
1.2bc
10. Tab
11. Ib
10. 3c
l.Sab
--
1.9ab
1968
'/liter
3.7b
1.8b
0.8a
O.T
1.5b
T.2d
14. 4b
12. Ib
10.2bc
1.9abc
--
1.3ab
2/
1969 Significance^-'
3
1
0
0
0
2
13
1
8
4
3
.5b
.4ab
.6a
.5
.6a
.Tc
.3b
.8a
. 4abc
.9d
--
.Ob
**
**
**
N.S.
**
**
**
**
**
A*
**
**
— ^proximate distance from sewage effluent application area.
-/ Significance of year effect: **, (P - 0.01); *, (P = 0.05); t, (P = 0.10); N.S. - not
significant, (P > 0.10).
—' Duncans separation of annual means at P = 0.05. Annual means having a common letter are
not different.
-------
Game lands Area
Introduction. Irrigation began in the Gamelands in November 1964 at
one site at a 4-inch rate and at two sites at a 6-inch application
rate. This continued until April 1965 when irrigation of the 6-inch
sites was changed to 4-inches per week. In August, 1965 all appli-
cation at the Gamelands site was terminated until November. At that
time the irrigation program was changed to a November-March period and
two additional sites, one a hay field and the other a forest area were
started with irrigation at two inches per week on a year-round basis.
The hay field site was terminated in Oct., 1969.
The soils have a higher sand content with occasional beds of relatively
clean sand being not uncommon. These beds may vary from 1 to 5 feet
in thickness and characteristically are interbedded with silt and clay
beds that make the deposits highly anisotropic with respect to perme-
ability. Slopes are gentle as a rule but> locally, wastewater is applied
where slopes exceed 6 percent. The sandy and stratified nature of the
soil results in some lateral flow of perched groundwater.
Monitoring Facilities
Deep Wells. Deep groundwater monitoring wells were drilled during the
initial site selection and evaluation study conducted in 1962. These
include G-l, 2, 3, and 6. Groundwater levels rapidly declined in the
region at the start of the drought in 1961. Gl, 2, 3 and 6 were dry
within less than a year and failed as monitoring wells. G-3 was
successfully deepened after going dry and was a rather reliable monitor-
ing well but too small in diameter to provide water level data after
installation of a pump. The other drilled wells, Gl, 2 and 6 which
had a final diameter of either 3 or 2 1/2 inches were not deepened
because of their small diameter, or because caving conditions and or
flowing sand were encountered.
G-3 is located on a single zone of fracture concentration at the center
and near the head of a dry underdrained karst valley. Six inches of
effluent were applied at weekly intervals to both valley walls the
first year November through August and four inches on a November through
.April basis during subsequent years. A 4-inch application rate was
used at the head of the valley as well.
Sidehill seepage along the lower segments of the valley and lower
reaches of the valley walls was rather abundant the first winter in
response to the 6-inch per week application rate. Runoff flowed past
G-3 nearly on a daily basis the first winter. In subsequent years,
after the irrigation rate had been cut to 4-inches per week, November-
April, surface seepage was greatly reduced but still noticeable.
329
-------
Subsequently G-12 was drilled in 1964 on a single zone of fracture
concentration to a final diameter of 6-inches and a depth of 300 feet.
At that point a bit was lost which precluded drilling any deeper. The
well had to be doubly cased to the total depth drilled to control flow-
ing sand. This well also went dry and failed to yield water samples
within less than a year of being drilled and remains inoperative to
present. It is located on the center line of the same valley but up
slope from G-3. The well did help to define the deep groundwater low
that underlies the Gamelands irrigation site.
G-10 was completed in 1966 at a 6-inch diameter. The well is doubly
cased, located on a zone of fracture concentration and down valley
from G-3. More than 80 feet of residual soil was encountered at the
drill site and 100 or more feet of unsaturated dolomite or sandy
dolomite bedrock.
Runoff from the irrigation site rarely extended beyond G-10. Rather,
water was captured in a diffuse manner by sandy soil with a forest
cover up valley from G-10.
A 2-inch per week open field irrigation site was operated from Nov.,
1965 to Oct., 1969 along one valley wall up slope to the south of G-10.
Despite the high topographic position of the Gameland irrigation area,
G-3 and 10 are both located in a groundwater low along which regional
groundwater flow is concentrated (Fig. 5 ). Their strategic location
along the center of a valley along which overland flow is concentrated,
position with respect to irrigated areas, and to zones of fracture
concentration that should channel reclaimed effluent to the monitoring
wells make it inevitable that both wells intercept effluent within the
groundwater reservoir before it leaves the Gamelands test area.
Water samples were bailed from G-3 the first year and were pumped from
G-3 and G-10 in subsequent years using small diameter piston pumps.
The pumps insured that more representative samples of groundwater were
obtained than if hand bailing methods were used.
Trench Lysimeter. A second sampling facility at the Gamelands was a
17-foot deep trench lysimeter which was placed near the base of a
valley wall mid way along the irrigation lines. No water samples were
collected prior to irrigation because the soil was too dry. Immediately
following the second week of irrigation, or after 12-inches of effluent
had been applied early in November, sidehill seepage became excessive
and the deep trench was flooded to ground level. Water levels were
controlled in the lysimeter pit using an electrical submergible pimp
and portable generator for part of 1965 and early 1966. The pit
remained flooded to various levels for more than a month during the
winter and early spring of 1966 and did not completely dry out until
irrigation was. stopped in August 1966. After installing a floor drain
and cutting back on the application level the lysimeter pit never
flooded again and continues to provide water samples to the present.
330
-------
Suction-Pressure Lysimeters. A network of stacked suction-pressure
lysimeters was installed at seven sites to replace the faulty sand-
point wells which failed to yield soil water samples the first year,
1964-65. Two each of these were located in the 6-inch and 4-inch per
week winter irrigated area one midway down slope and one at the bottom
of a slope in a region of noticeable runoff. Three other stacks of
suction-pressure lysimeters were placed in two 2-inch per week year-
round irrigated areas, one in an open field site and two in a forested
site.
Suction pressure lysimeters were stacked two or more to a drill hole
(6) at approximately 5 foot intervals from depths of 6 to 26 feet.
These have provided rather reliable samples until 1970 except during
dry months in the non-irrigation period on the winter irrigation sites.
Water Quality
Deep Wells Quality. Figures 93, 94 and 95 display the percent of
samples that equalled or exceeded stated Cl, NOj-N, and apparent ABS
values for G-3. Chloride levels were in the background range during
1965 and 1966 and began to show an increase by 1967 indicating that
approximately five years were required for the reclaimed effluent to
appear in local groundwater in sufficient volume to be detected.
Chloride concentrations changed from a median of 2.7 ppm in 1965, and
2.0 ppm in 1966 to 12 ppm in 1967 and 1968. Eighty percent of the
chloride values equalled or exceeded 2 ppm in 1965, 1.8 ppm in 1966,
11 ppm in 1967 and 7.0 ppm in 1968. Only 20% of the chloride concen-
trations equalled or exceeded 14 ppm in 1967 and 23 ppm in 1968 and
were well within acceptable potable water limits during each sampling.
1967 and 1968 chloride data for G-10 show similar results with a median
value of 11 ppm for 1967 and 13 ppm for 1968. Eighty percent of the
chloride values in G-10 equalled or exceeded 12.5 ppm in 1967, and 15
ppm in 1968. These values were slightly lower than for G-3 because G-3
is more centrally located within irrigated areas. Groundwater in the
vicinity of G-3 should receive less dilution and show less influence
of dispersion than would be true near G-10.
Nitrate-nitrogen concentrations for G-3 also showed an increase by the
fifth year of irrigation (Fig. 94) and continue to remain above initial
background levels to the present. This well should have felt the full
brunt of the excessive irrigation amount of 6 inches of effluent per
week the first year because sidehill seepage was concentrated on both
valley walls near G-3. Surface runoff has continued to occur along
the center of the valley near G-3 each winter and approaches 5 to more
than 30 gpm for short periods of time before infiltrating further down
the valley floor.
The median nitrate-nitrogen value was as low as 0.52 ppm in 1965 and
0.54 ppm in 1966, which can be considered as background. These values
331
-------
o 10
£
o>
•o
Monitoring Well G-3
1 2 5 10 20 50 80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 93. Percent of G-3 Deep Well Samples with. Chloride
Concentrations Equalling or Exceeding Stated Values.
332
-------
Monitoring Well 6-3
0.01
50
80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 94. Percent of G-3 Deep Well Sahples with, N03-N Concentrations
Equalling or Exceeding Stated Values.
333
-------
increased to 4.4 ppm in 1967 and then dropped to 1.8 ppm in 1968. The
slight reduction in 1968 compared to 1967 may reflect slow but in-
creased dilution of groundwater related to increased precipitation in
1967 and 1968 and the decrease in application amounts following the
first year of irrigation.
Compared to 1965 and 1966 values there can be little doubt that nitrate
increases were related to the irrigation project because flow of
groundwater within the regional groundwater low located below the
Gamelarids site is positioned largely beneath forested areas and aban-
doned farm land. The general lack or limited area of agricultural
lands in the region of recharge rules out agricultural activity as a
source of nitrates. Also few homes are present within the recharge
area, hence septic tanks were not an important source of nitrates.
Unimportant changes in apparent ABS and phosphorus were noted in G-3
and G-10 (Fig. 95) for the period of available record.
The median ABS values in G-3 were 0.1 ppm in 1965, .04 ppm in 1966,
.07 in 1967, and 0.1 ppm in 1968. These are within the background
range. Similarly, phosphorus concentrations remained low and within
the background range. The median values were less than .01 ppm in
1965 and 1966, 0.04 ppm in 1967 and 0.02 ppm in 1968. Similar and
insignificant differences in ABS and phosphorus were noted for G-10
during 1967, 1968 and 1969.
The year effects for phosphorus, nitrate-nitrogen and chloride G-3
and G-10 are shown in Tables 149-151. For phosphorus, the year effect
was not significant for both wells. With respect to NO?-N the year
effect was highly significant (P = 0.01) for G.-3 but only significant
(P =0.05) for G-10. The N03-N concentrations in 1968 and 1969 were
both significantly less than in 1967 but not significantly different
from each other. This was probably a reflection of the decreased
effluent loading which began in Nov., 1965.
The chloride data for G-3 and G-10 show the strongest year effects,
being highly significant (P = 0.01) for both wells. In G-3 the
chloride levels appear to have peaked out at less than 15 mg Cl jjer
liter although the mean annual effluent concentration has remained
fairly constant in the range of 40-50 mg Cl per liter. On the
other hand in G-10, which is more remote from the irrigated area,
the chloride concentration has decreased substantially from 1968
to 1969, dropping from 12.1 to 1.8 mg Cl/1. This drop is probably
related to the lower irrigation load on the hay field adjacent to
G-10 in 1968 combined with the earlier decreased load on the area
surrounding G-3 which lies up-slope from G-10.
334
-------
Monitoring Well G-3
0.001
12 5 10 20
80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 95. Percent of G-3 Deep Well Samples with ABS Concentrations
Equalling or Exceeding Stated Values.
335
-------
Trench Lysimeter Quality. Trench lysimeter data reveal that the 6-
inch application rate the first year caused the chloride concentra-
tion to build up almost immediately after irrigation began in Nov,
1964. Table 152 and Figures 96-98 show the 20%, 50% and 80% values
equalled or exceeded for 1965 through 1968' for the 5, 10 and 14 foot
depths. Samples were collected at 1-foot intervals to 17 feet but
all data are not shown to avoid repetition. It may be seen that the
chloride concentrations were lowest in 1965 at all depths and that
these increased by approximately 10 ppm in 1966. No background
values for chloride were obtained from the trench lysimeter because
no soil-water samples were obtained until after 12-inches of efflu-
ent were applied. However in a nearby control area chloride values
in pan and section lysimeters rarely exceeded 3mg/l. It may be
seen that the 14-foot deep samples show slightly higher chloride
values than the 10 foot sampling depth. Lateral flow was particu-
larly pronounced around the 14-foot depth. Water frequently
continued to flow down slope into the sample pit at this depth
after flow ceased at shallower sampling points. Water quality
'variations at this depth might be expected to be related to recharge
up slope and prolonged lateral flow more so than from vertical
percolation immediately above the pan lysimeters.
Table 153 and Figures 99-101 show the nitrate-nitrogen values
equalled or exceeded by 20%, 50% and 801 of the samples at 5, 10
and 14 feet for 1965 through 1968.
Table 152. Chloride Concentrations Equalled or Exceeded by 20%, 501,
and 80% of the Values for 5, 10,-and 14 foot Depths in
the Gameland's Trench Lysimeter (SGL).
Values Equalled or Exceeded by Various Proportions of Values
1965 1966 1967 1968
20% 50% 80% 20% 50% 80% 20% 50% 80% 20% 50% 801
Depth in Ft mg Cl" per liter
5 46 43 40 56 52 47 62 54 50 60 50 41
10 44 39 30 55 49 46 58 51 46 54 42 37
14 44 42 38 57 51 46 - - - 55 43 39
336
-------
too
o>
Q_
o 10
Q_
O>
JO
i_
_o
o
J L
I I i i I I
I .2 5 10 20 50 80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 96. Percent of Deep Trench Lysimeter (SGL) Samples at the
Hve-^ot Depth With Chloride Concentrations Equalling
or'Exceeding Stated Values.
337
-------
100
CD
Q_
CO
a
Q_
c
CD
o
10
1 I I
SGL-IO'
I 2 5 10 20 50 80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 97. Percent of Deep Trench Lysimeter (SGL) Samples at the
Ten-foot Depth With Chloride Concentrations Equalling
or Exceeding Stated Values.
338
-------
100
c.
o
CL
to
S 10
Q_
C
o>
•o
_o
JC
o
I I I I I
I 2 5 10 20 50 80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 98. Percent of Deep Trench Lystmeter (SQL) Samples at the
14-foot Depth With Chloride Concentrations Equalling
or Exceeding Stated Values.
339
-------
Table 153. Nitrate-Nitrogen Concentrations Equalled or Exceeded by
20%, 50%, and 80% of the Values for 5, 10, and 14 foot
Depths in the Gameland's Trench Lysimeter (SGL).
Values Equalled or Exceeded by Various Proportions of Values
1965 1966 1967 1968
20% 50% 80% 20% 50% 80% 20% 50% 80% 20% 50% 80%
Depth in Ft mg NOj-N per liter
5 6.8 3.8 2.8 24 20 13 28 25 21 - 24 19 17
10 14.0 7-0 2.5 31 20 16 30 22 16 28 23 20
14 14.0 10.0 3.8 25 20 17 - - - 29 22 19
Nitrates like the chlorides moved rapidly and deeply through the soil
in response to the 6-inch per week overload. The median (50%) values
increased strongly with depth in 1965, just reaching the U.S.P.H.S.
potable water limit of 10 mg NOg-N at 14 feet. However in 1966, 1967
and 1968 the median values approached a constant value of approximately
20 mg N03-N at all depths even though the effluent load was cut to 4
inches per week and applied only during the Nov-March period. The
decreased biological activity of both trees and microbes during the
cold part of the year probably contributed to the greater breakthrough
of nitrate.
Despite the overload of effluent in 1964-65 phosphorus concentrations
remained low at all depths indicating the high degree of adsorption and
renovation that can be achieved for this constituent even on a sandy
soil. Values were all in the background range in 1965 and 1966 (Table
154 and Figures 102, 103, and 104) and showed a slight increase at the
10-foot depth in 1967 and at the 10 and 14 foot depth in 1968. These
slight increases may reflect a slight breakthrough at these depths
because of the prolonged lateral flow from up slope. The median
values in 1968 after four years of heavy irrigation were 0.01 at the
5-foot depth, 0.14 at the 10-foot depth, and 0.12 at the 14-foot
depth.
340
-------
c
o
co
t_
o
Q_
c
CO
o
I 2 5 10 20 50 80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 99. Percent of Deep Trench Lysimeter (SGL) Sajiples at the
Five-foot Depth With: H03-N Concentrations Equalling
or Exceeding Stated Values.
341
-------
100
1 2 5 10 20 50 80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 100, Percent of Deep Trench Lyslmeter (SGL) Samples at the
Ten-foot Depth With NO^-N Concentrations Equalling
or Exceeding Stated Values.
342
-------
&
CO
o
Q_
CO
o
I 2 5 10 20 50 80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 101, Percent of Deep Trench Lysimeter (SGL) Samples at the
14-foot Depth With N03-Nc Concentrations Equalling or
Exceeding Stated Values.
343
-------
I—I 1—I 1—I—I—I—I—I—I 1 1
0.001
I 2,5 10 20
80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 102, Percent of Deep. Trench Lysimeter (SGL) Samples at the
Five-foot Depth With. P Concentrations Equalling or
Exceeding Stated Values.
344
-------
0.001
50
80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 103, Percent of Deep Trench Lysimeter (SGL) Samples at the
Ten-foot Depth With P Concentrations Equalling or
Exceeding Stated Values. .
345
-------
I 1—I 1—I—I—I—I—I—I I I
0.001
80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 104. Percent of Deep Trench Lysimeter (SGL) Samples at the
14-foot Depth With P Concentrations Equalling or
Exceeding Stated Values.
346
-------
Table 154. Phosphorus Concentrations Equalled or Exceeded by 20%,
50%, and 80% of the Values for 5, 10, and 14 foot Depths
in the Gameland's Trench Lysimeter (SGL).
Values Equalled or Exceeded by Various Proportions of Values
1965 1966 1967 1968
20% 50% 80% 20% 50% 801 201 50% 80% 20% 50% 80%
Depth in Ft mg P per liter
5 .020 .005 .002 .022 .012 .003 .027 .013 .003 .032 .010 .003
10 .012 .004 .002 .030 .013 .005 .190 .084 .017 .220 .140 .030
14 .030 .010 .002 .052 .030 .008 - - - .150 .120 .030
ABS data (Table 155 and Figures 105, 106 and 107) clearly show the
influence of overloading the first year. The mean concentration in the
applied effluent was 1.61 ppm in 1965, 0.40 ppm in 1966, 0.36 ppm in
1967, and 0.56 ppm in 1968. The values equalled or exceeded by 50% of
the values in 1965 are only slightly below that in the applied effluent
at the 5-foot depth and attenuated with depth. In 1966 with a lower
concentration in the applied effluent the cut back in application
amounts from 6 to 4-inch per week was still excessive and no decrease
in concentration occurred at 5 feet. The 1967 and 1968 ABS data how-
ever do show substantial decreases indicating that the renovation media
had been flushed of earlier ABS build up. The 1967-1968 data are more
in line with what would be expected if some degree of renovation was
being achieved.
Suction Lysimeter Quality. Data are presented only for two suction
lysimeter sites. One, SLG-1, was located in the New Gameland Hardwood
Area which has been receiving two inches of effluent weekly, year-
round since November of 1965 and the other, SLK-1, was located in a
cropland area in the Gamelands which has been farmed in a rotation, of
red clover hay (1966, 1967) and corn (1968) and received two inches of
effluent weekly, year-round from July, 1965 until Oct, 1969. Data are
347
-------
I—I—I—I—I—I—I
0.01
12 5 10 20
80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 105. Percent of Deep Trench Lysimeter (SGL) Samples at the
Five - foot Depth With ABS Concentrations Equalling or
Exceeding Stated Values.
348
-------
£
en
CO
CD
0.01
12 5 10 20
80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 106. Percent of Deep Trench Lysimeter (SGL) Sanples at the
Ten-foot Depth With ABS Concentrations Equalling or
Exceeding Stated Values.
349
-------
10
CO
CD
O.I
0.01
I I I
I I
SGL-14'
I I I I I
12 5 10 20
50
80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 107. Percent"of Deep Trench Lysimeter (SGL) Samples at the
14-foot Depth With ABS Concentrations Equalling or
Exceeding Stated Values.
350
-------
\
Table 155. ABS Concentrations Equalled or Exceeded by 20!,"50% and
80% of the Values for 5, 10, and 14 foot Depths in the
Gameland's Trench Lysimeter (SGL).
Values Equalled or Exceeded by Various Proportions of Values
1965 1966 1967 1968
20% 501 80% 20% 50% 80% 20% 50% 80% 20% 50% 80%
Depth in Ft mg ABS per liter
5 1.40 1.30 1.05 0.80 0.40 0.32 0.30 0.21 0.08 0.36 0.15 0.10
10 1.35 0.95 0.45 0.45 0.33 0.26 0.28 0.18 0.09 0.28 0.18 0.10
14 1.30 0.78 0.50 0.31 0.28 0.23 - - - 0.30 0.18 0.12
presented for phosphorus, nitrate-nitrogen, chloride and ABS at the 6-,
10.4-, 17.5-, and 20.3-foot depths for SLG-1 and for nitrate-nitrogen
at the 7-, and 18-foot depths for SLK-1.
The phosphorus data in Table 156 and Figures 108-109 indicate that the
median value at the various depths has remained relatively unchanged
or decreased with time and has remained within the background range.
In 1968 the median values were 0.013, 0.003, 0.016 and 0.010 mg P/l,
respectively, at the 6-, 10.4-, 17.5-, and 20.3-foot depths.
Table 156. Phosphorus Concentrations Equalled or Exceeded by 20%, 50%
and 80%, of the Values for 6-, 10.4-, 17.5- and 20.3-foot
Lys imeters (SLG-1).
Values Equalled or Exceeded by Various
of Values
Depth in Ft
6
10.4
17.5
20.3
20%
.055
.095
-
.082
1966
50%
.022
.030
-
.025
80%
.006
.010
-
.007
20%
mg P
.068
.044
.062
.065
1967
50%
80%
Proportions
20%
1968
50%
80%
per liter
.017
.015
.025
.027
.002
.002
.004
.002
.032
.014
.022
.035
.013
.003
.010
.010
.002
.002
.003
.002
351
-------
II I I I I I I 1 I
2 5 10 20 50 80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 108, Percent of Deep Suction Lysiroeter (SLG-1) Samples at
the Six-foot Depth With P Concentrations Equalling or
Exceeding Stated Values.
352
-------
I I I I—I 1—I—I 1—I
SLG-I at 17.5'
o.ooi
80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 109. Percent of Deep Suction Lysijneter (SLG-1) Samples at
the 17.5-fbot Depth With P Concentrations Equalling
or Exceeding Stated Values.
353
-------
ABS values in Table 157 and Figures 110-111 are also well within
background limits and have no importance for water quality consider-
ations .
Table 157. ABS Concentrations Equalled or Exceeded by 201, 501 and
80% of the Values for 6-, 10.4-, 17.5- and 20.3-foot
Lysimeters (SLG-1).
Values Equalled or Exceeded by Various Proportions
of Values
1966
20% 50% 80%
Depth in Ft
6 0.18 0.08 0.03
10.4 0.09 0.08 0.01
17.5
20.3 0.08 0.05 -
1967
20%
mg
0
0
0
0
ABS
.11
.14
.07
.08
50%
80%
20%
1968
50% 801
per liter
0
0
0
0
.03
.05
.03
.05
0
0
0
0
.01
.03
.01
.08
0.
0.
0.
0.
23
11
13
08
0
0
0
0
.07
.07
.06
.03
0.03
0.04
0.03
0.01
The values for chlorides and nitrate-nitrogen in Tables 158 and 159
and Figures 112, 113, 114, 115 indicate that chlorides had already
broken through at all depths in 1966 and that although nitrates had
increased substantially over background values by 1966 they increased
even more substantially in 1967 and 1968. The lag of nitrate behind
chloride is probably due to biological retention and recycling of
nitrogen through the forest stand.
The median values for chloride at the 20.3-foot depth were 35, 22, and
20 mg Cl'/l, respectively, in 1966, 1967 and 1968. For nitrate-
nitrogen the median values in 1966, 1967 and 1968 were, respectively,
4.0, 14 and 16 at the 6-foot depth, and 3.7, 11 and 20 at the 20.3-foot
depth.
The nitrate and chloride values in the suction lysimeters at 6 and
10.3 feet are similar to those found in the trench lysimeters at simi-
lar depths. At both sites overloads and undesirable breakthrough of
nitrates occurred after approximately 100 inches of effluent had been
applied either on a part-year basis at the trench lysimeter site (SGL)
or on a year-round basis at the suction lysimeter site (SLG-1).
354
-------
c=
o
o
Q_
CO
GO
I I 1 1 1 1 1
2 5 10 20 50 80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure. 110, Percent of Deep Suction Lysimeter (SLG-1) Samples at
the Six-foot Depth With ABS Concentrations Equalling
or Exceeding Stated Values.
355
-------
CD
o_
CO
o
Q_
CO
GO
SL6-I at 17.5'
I 2 5 10 20 50 80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 111. Percent of Deep Suction Lysimeter (SLG-1) Samples at
the 17.5-foot Depth With ABS Concentrations Equalling
or Exceeding Stated Values.
356
-------
Table 158. Chloride Concentrations Equalled or Exceeded by 20%, 50%,
and 80% of the Values for 6-, 10.4-, 17.5-, and 20.3-foot
Lys imeters (SIG -1).
Values Equalled or Exceeded by Various Proportions
of Values
Depth in Ft
6
10.4
17.5
20.3
20%
48
52
--
42
1966
50%
45
32
--
25
1967
80%
43
23
--
22
20%
mg Cl"
43
50
55
37
50%
per
41
47
49
32
80%
liter
38
46
45
21
20%
47
48
49
25
1968
50%
43
46
46
20
80%
41
45
44
17
Table 159. Nitrate-Nitrogen Concentrations Equalled or Exceeded by
20%, 50% ^nd 80% of the Values for 6-, 10.4-, 17.5-, and
20.3-foot Lysimeters (SLG-1).
Values Equalled or Exceeded by
of Values
1966 1967
20%
50%
80%
Depth in Ft
6
10.4
17.5
20.3
4.5
5.0
--
5.5
4.0
4.6
—
3.7
0.3
0.3
--
1.8
20%
50%
mg NOj-N per
15
25
22
15.5
14
21
15
11
Various Proportions
1968
80%
liter
10
12
9.8
6.8
20%
20
27
30
25
50%
16
24
21
20
80%
15
20
18
17
Nitrates in the hay field site (SLK-1) (Table 160) were substantially
less than in the hardwood forest site (SLG-1) at similar depths. In
1966 the SLK-1 median value was 1.1 mg N03-N/1 at 7 feet whereas the
1966, SLG-1 median value was 4.0 mg N03-N/1 at 6 feet. In 1968 the
SLK-1 median nitrate value was 8.6 at 18 feet and the SLG-1 median
nitrate value was 21 mg NO,-N/1 at 17.5 feet. The almost two-thirds
lower NOX-N in the cropland site was probably due to the removal of
nitrogen in the harvested crops and possibly some denitrification.
The SLK-1 site had more clay in the subsoil which caused intermittent
357
-------
100
cu
Q_
CO
o
Q_
10
O
I I
SLG-I at 6'
I I
I 2 5 10 20 50 80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 112. Percent of Deep Suction Lysimeter (SLG-1) Samples at
the Six-foot Depth With Chloride Concentrations
Equalling or Exceeding Stated Values.
358
-------
1000
Q_
to
"5 100
Q_
_c
o>
10
T I I I i i i i i
SLG-I of 17.5'
I 2 5 !0 20 50 80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure. 113. Percent of Deep Suction Lysimeter (SLG-1) Samples at
the 17.5-foot:.Depth. With.Chloride Concentrations
Equalling or Exceeding Stated Values.
359
-------
100
CO
o
Q_
c
t/>
o
10
i i
SLG-I at 6'
I I
I I I I
I 2 5 10 20 50 80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 114. Percent of Deep Suction Lysimeter (SLG-1) Saiiples at
the Six-foot Depth With .N03-N Concentrations Equalling
or Exceeding Stated Values.
360
-------
100
I I I I 1—I—I—I—I—I—I 1—I
SLG-I at 17.5
I 2 5 10 20 50 80 90 95
Percent of Samples With a Concentration
Equaling or Exceeding the Stated Value
Figure 115. Percent of Deep Suction Lysimeter (SLG-1) Samples at
the 17:5-foot: Depth:With .N03-N Concentrations
Equalling of Exceeding Stated Values.
361
-------
perching of a shallow water table at a depth of 15 to 20 inches as
found by Rebuck (15). Such a hydrologic situation provides conditions
favorable to denitrification.
Table 160. Nitrate-Nitrogen Concentrations Equalled or Exceeded by
20%, 50% and 80% of the Values for a Suction Lysimeter,
SLK-1, in a Croplandi/ Area at the Gamelands Which
Received Two Inches of Effluent Per Week, Year-Round,
Since July, 1965
Values Equalled or Exceeded by Various Proportions
of Values
1966 1967 1968
20% 50% 80% 20% 50% 80% 20% 50%
Depth in Ft mg N03-N per liter
7 4.5 1.1 0.3 15 11 5.5 -
18 - 8 5.6 3.6 79 8.6 6.1
-' Red clover hay in 1966 and 1967, corn in 1968.
In general the suction and pan lysimeter data agree fairly well that
nitrate-nitrogen concentrations in the forested sandy soils of the
Gamelands Area could be a constraining parameter since concentrations
in the soil water exceed the U.S. Public Health Service recommended
limit within two years if two inches of effluent is applied at weekly
intervals year-round or within one year if four or six inches were
applied at weekly intervals for five to six months out of a year. On
the other hand the deep well data indicate that concentrations in the
well samples remained below U.S.P.H.S. recommended limits. Either
the deep wells are not sampling the recharging wastewater, or the
latter is being diluted during pumping, or the recharging wastewater
is being diluted by recharge flowing from surrounding unirrigated
areas into the irrigated area. In any event it would appear more
definitive to use the shallow on-site suction lysimeters as indicators
of the treatment level attained for weakly absorbed anions and cations.
For strongly adsorbed anions like phosphorus and cations such as the
heavy metals additional attenuation of concentration can be expected
over the entire path length of flow.
362
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GROUND WATER RECHARGE AND REUSE
General Considerations
Sites can be selected with wastewater renovation as the sole purpose
or with the added possibility of reuse. Parizek and Myers indicated
that site selection criteria for a renovation system favoring distant
reuse may be different from those favoring local reuse as groundwater.
Shallow penetration of renovated effluent and rapid return to the
surface may be acceptable. This can be achieved by irrigating side
hill slopes and local uplands that favor the surface return of waters
after a sufficient degree of treatment has been achieved. Irrigation
on local uplands surrounded by nearby valleys and on stratified
deposits favoring the development and lateral movement of perched
groundwater are common settings where this can be achieved. Loess
overlying glacial till, shale or siltstone bedrock, lake clay, lake
silts and sands, fluvitile silts and sands, dune sand, residual and
other transported soils that overlie deposits with low permeability
characteristics are cases in point. The percentage of land area that
would favor renovation but unimportant groundwater recharge is greater
for many states than is land that would favor significant increases in
groundwater recharge for local reuse.,
Groundwater recharge for local reuse may be an important objective at
some project sites. Examples have been cited above where infiltra-
tion, renovation, and quick return to land surface can be achieved.
In these cases, reclaimed effluent may be available for reuse off-site
as surface water, it may be recaptured by wells located downstream by
induced streambed infiltration, it may be used as surface water for
recreational purposes or wildlife propagation or as irrigation water.
Water supply wells may be located beneath or adjacent to irrigation
sites to derive benefits of reclaimed water. Wells may be planned to
improve drainage as well as to supply water. In both instances, the
number and spacing of wells required to provide the necessary amount
of water will depend upon aquifer characteristics -- storage, trans-
mission 'properties, hydrologic boundary conditions, recharge rates --
and degree of treatment anticipated, amount of land to be irrigated,
application rates and evapotranspiration requirements.
The number and spacing of onsite wells necessary to insure drainage
may depend upon the depth and extent of pumping cones of depression
developed for each well, which is related to the number and spacing
of wells and aquifer hydrologic characteristics.
Pumping cones of depression within the free-water surface or water
table are ideal for dewatering some unconfined soil and rock aquifers
and for deriving direct benefit from artificial recharge. Four plans
of action are possible: (1) a wastewater renovation facility can be
363
-------
located adjacent to an existing well field where site conditions are
suitable for irrigation, and effluent used is free of toxic or harmful
nondegradable substances that are not likely to be removed in the
renovation media, (2) a well field can be placed in close proximity of
the site after it has been established that adequate renovation is
being achieved, (3) reclaimed water discharged to surface can be re-
collected in wells relying upon induced streambed infiltration, or
(4) drainage wells can be placed within the irrigation area with no
beneficial use planned for the water except to insure adequate
drainage.
For all four cases, unconfined aquifers, or at least, semi-unconfined
aquifers should underlie the irrigation site. These may be of diverse
origin and be composed of fractured bedrock (sandstones, siltstones,
carbonate rocks, gneisses and schists) sedimentary rocks containing
favorable intergranular or primary permeability (sandstone, siltstone,
carbonate rocks) or permeable unconsolidated sediments such as sand
and gravel.
Confined aquifers where confining beds are thick or relatively low in
permeability, may derive very little more recharge than was being
achieved under natural conditions. Once the maximum hydraulic gradient
has been developed between the source bed and confined aquifer in
response to recharge and pumpage, vertical leakage rates are fixed.
Where recharge rates to source beds are in excess of the vertical leak-
age rate to the confined aquifer, water is rejected from the shallow
system and no additional recharge benefits are achieved (9).
Vertical flow rates through confining beds to underlying aquifers can
be computed using a form of Darcy law.
hA ( 1 )
where: Q = leakage rate through the confining bed in gallons per
day Cgpd).
P1 = vertical hydraulic conductivity of confining bed, in
gallons per day per square foot (gpd/ft2).
m' - saturated thickness of confining bed in feet.
h = difference in the mean hydraulic head in the aquifer and
in the source bed overlying the confining layer, in feet.
A = area of confining bed through which leakage is occurring
in square feet.
Selected vertical hydraulic conductivities for soil and rock units are
given by Parizek (9).
364
-------
Groundwater Recharge
The amount of renovated effluent recharged to the groundwater reservoir
was estimated from data available on the total amount of effluent and
rainfall applied on the plots during the irrigation period, and poten-
tial evapotranspiration estimated by the Thomthwaite and Mather (99,100)
method. Recharge ranged from 1.1 to 1.8 million gallons per acre with
an average of 1.6 million gallons (Table 161). Averaged over the
seven year interval recharge amounted to approximately 95 percent of
the effluent applied at the 2 inches per week rate.
Recharge rates were higher when water was applied during years with
normal or above normal rainfall or throughout the year. Evapotrans-
piration losses ate greatly diminished during the late fall, winter,
and spring and more of the water infiltrating into the soil from
natural precipitation and irrigation is potentially available for
groundwater recharge. Maximum recharge amounts from applied effluent
approximate 2.8 million gallons per acre where 2 inches per week are
applied on a year around basis.
Runoff which did occur at the irrigation sites following snow and ice
pack melt or heavy or prolonged rains was ponded in one or more closed
surface depressions where it was captured by infiltration or it infil-
trated in adjacent unirrigated buffer areas which were usually in
forest cover. Closed depressions were numerous on all of the upland
areas selected for irrigation or they were available downslope from
test plots, hence detention storage was provided naturally. This
would not necessarily be true at other irrigation sites where deten-
tion storage would have to be engineered to prevent or eliminate
runoff.
It was found that adjacent border areas with forest stands were ideal
to help contain runoff and promote infiltration all seasons of the
year. Rarely did overland flow extend more than 100 feet beyond irri-
gation plots during the spring thaw.
Effect of Recharge on Water Levels
Recharge amounts are still somewhat limited at the experimental sites
due to their relatively small size. Only 500,000 gallons of effluent
are being applied per day divided between two locations 1% miles apart.
Moreover, recharge at the Agronomy-Forestry site has not been suffi-
cient to maintain the elevation of a local groundwater mound (Figs.
4 § 5) which existed before irrigation was started. Water level
declines noted in Figure 116 show that recharge was not sufficient to
reverse the downward water level trend in the immediate vicinity of
the Agronomy-Forestry site. The rate and amount of decline was slowed
but still dominated by a downward trend related to the drought (1961-
1967), to continued groundwater discharge to springs and to prolonged
pumping from the nearby University well field.
365
-------
t»
Table 161, Estimates of Recharge to the Groundwater Reservoir on Each Acre Receiving Two Inches
of Effluent Per Week.
Irrigation No. of Effluent
Period Irrigations Applied
June 18 -Dec 5, 1963
Apr 8-Nov 18, 1964
Apr 20-Nov 16, 1965
Apr 5-Nov 15, 1966
Apr 18-Oct 31, 1967
Apr 9-Nov 12, 1968
Apr 15-Oct 29, 1969
Average
23
33
31
32
28
32
21
gallons/acre
1,249,000
1,792,000
1,684,000
1,738,000
1,521,000
1,738,000
1,140,000
Rainfall
PEli/
gallons/acre
447,500
460,800
444,800
553,900
745,600
700,000
589,500
583,500
650,800
635,800
637,900
407,600
591,000
396,000
Groundwater
Recharge '•
gallons/acre
1,113,000
1,602,000
1,493,000
1,654,000
1,859,000
1,847,000
1,333,500
1,557,000
2/
1 Recharge-'
89
89
89
95
100
100
100
95
— Potential evapotranspiration calculated by method of Thornthwaite and Mather (99,100)
2/
—' Expressed on basis of effluent applied
-------
Elevation of Water Table
Above Mean Sea Level in Feet
(F-3) On Site Monitoring Well
23 Private Well Adjacent to Agronomy Area
and University Well Field
UN-14 University Water Supply Well Adjacent
to Agronomy - Forestry Area
I I I I I I I I I I I I I I I I I I I I I I
1963 Jan. 1964
Month and Year Water Levels Measured
I I I I I I I
1962 Jan.
I I I I I
1965
Figure 116. Water Level Declines in Selected Wells.
-------
Water levels recorded in F-3 located immediately downslope from the
Agronomy-Forestry site showed a steady decline during the period 1962
to May 1965 until it failed as a monitoring well (Fig 116). A private
well (W-23) showed a similar trend until it failed during September
of 1965. With return to near normal or above normal precipitation
starting in 1967, groundwater levels have begun to recover on a slow
but persistent basis. Well 23 was reopened in April 1973 and the
water level had recovered by more than 72 feet since September 1965.
Water levels in UN-14, potentially the principal benefactor of re-
claimed effluent at the Agronomy-Forestry site, did not decline as
drastically as W-23. This well has been pumped nearly continuously
since 1963 when it was first put into service and has also responded
to the wetter years since 1967.
As an alternate to direct measurement of the water table buildup
resulting from recharge, which could not be determined, recharge
effects have been computed using recharge amounts determined by the
Thornthwaite or Blaney-Griddle methods and the best estimates of
aquifer storage and transmission characteristics evaluated from field
pumping tests and by regional groundwater depletion studies.
The computed water level responses must be considered as approximate
in view of the anisotropic nature of the aquifer system involved and
the methods used to compute aquifer storage and transmission character-
istics .
The residual mound that should be attributed to recharge from spray
irrigation cannot be computed exactly because the permeability and
storage properties of the fractured dolomite and sandy dolomite
•aquifer that underlie the site cannot be determined precisely using
existing analytical techniques. Pumping tests were conducted on
University water supply wells for this purpose (UN-2, 14, 16, 17, 20,
24, 25 and 26) and best estimates of coefficients of storage and
transmissivity are summarized in Table 162. Coefficients of trans-
missivity ranged from a high of 58,000 in a test (not shown in Table
162) to a low of 5260 gpd/ft depending^ upon whether a production or
observation well was located on a single zone of fracture concentra-
tion, at the intersection of two zones of fracture concentration or
in adjacent more massive and less jointed rock.
The cone of depression tends to migrate more rapidly along avenues of
high permeability causing more drawdown along these zones than for
points the same distance from the pimped well but located in adjacent
more massive blocks of rock. Small drawdown values obtained from
observation wells located in less productive rock but close to the
pumped well will yield computed transmissivity values in the vicinity
of the observation well that frequently are lower than when the obser-
vation wells are later pimped and other observation wells are used to
368
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obtain time-drawdown data. This discrepancy is shown in Table 162
for the case of UN-25 which yielded a transmissivity value of 32400
as an observation well during a production test on UN-2, and a 3370
value when UN-25 was pumped. The anisotropic character of the local
aquifer is obvious from these data.
Coefficients of storage determined from these same pumping tests
ranged from 1.4 x 10-3 to 5.6 x 10-5. These seemingly low values are
typical of. carbonate aquifers in central Pennsylvania and are in the "
artesian range despite the fact that the aquifer is under water table
conditions. Coefficient of storage values are expected to be slightly
higher than those computed from these 24 to 48 hour pumping tests
because when these fractured rocks are subjected to prolonged periods
of drainage of a week or more storage values should increase. The
delayed drainage would occur from vugs, minor fractures and inter-
granular openings.
Gravity yield values which are a measure of the storage properties of
soil and rock have been determined by an alternate method for all of
the carbonate and non-carbonate rocks in Spring Creek basin drained
during a given period of groundwater depletion. The irrigated areas
are included in this basin which is approximately 175 square miles in
area. Groundwater runoff was determined using a mean groundwater
stage, groundwater runoff rating curve prepared when all flow leaving
the basin was known to be groundwater. Gravity yield was determined
using the relationship:
Sg = H (Yg) (2)
Where Sg is the change in groundwater storage during an inventory
period
H is the corresponding change in mean groundwater stage and
Yg is the gravity yield.
the gravity yield of a rock or soil after saturation or partial satur-
ation is taken as the ratio of the volume of water it will yield by
gravity to its own volume, during a given period of groundwater
recession.
During periods of recession, in which there is no recharge and no
surface runoff, the change in groundwater storage is approximately
equal to the volume of groundwater runoff, as measured at the stream
gaging station.
An average gravity yield of 1.5% was computed for the volume of rock
dewatered during the period of water table decline. For prolonged
periods of drainage the ultimate gravity yield value is equal to the
specific yield. The specific yield is the ratio of the volume of
water which soil and rock will ultimately yield by gravity to the
volume of soil and rock.
369
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Table 162. Selected Values for Coefficients of Transmissivity and
Storage Obtained from Pumping Tests Conducted in the
University Well Field (Modified from S. H. Siddiqui, 1969)
(101)
With UN-2 as a pumping well
Observation Wells Average Coefficient of , / Average Coefficient
Transmissivity (gpd/ft)- of Storage xlO5
UN-3
UN-26
UN- 4
UN-25
UN- 16
UN-20
14,800
35,500
21,200
32,400
2,700
37,650
14.0
5.6
140.0
90.0
30.0
90.0
Mean 24,000 Mean 60.0
With UN-25 as a pumping well and observation well
Observation Wells Average Coefficient of , / Average Coefficient
Transmissivity (gpd/ft)— of Storage ^
UN-25
UN-4
UN-3
3,370
4,360
3,260
70.0
30.0
9.0
Mean 3,663 Mean 36.0
— Average values of coefficients of transmissivity and storage are
based on semi-log time drawdown and log log time-drawdown methods
of analysis.
Parizek (102) and Konikow (103) have shown that both values can vary
with the mean depth of the water table and that normally these decrease
as the depth to the water table increases in fractured rocks.
The 1.5% average regional gravity yield value is considered as being
slightly too low for the aquifer beneath the irrigation plots. The
Upper Sandy Dolomite member of the Gatesburg Formation contains 5 to
35 foot thick beds of dolomitic sandstone, sandy dolomite and loosely
cemented sandstone interbedded with fine-to coarse-grained dolomite.
Drill cores obtained from this formation at the Agronomy Forestry site
and Gamelands site were tested for porosity. Intergranular and vug
porosity contained in core samples were included in testing for porosity
while enlarged openings along bedding planes, joints and along selected
bedrock units were excluded by nature of the sampling procedure used.
370
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Smith (104) studied porosity development using cores of the Gatesburg
Formation in the genetically related sedimentological system quartz
sandstone-dolomite. Both quartz sandstone and nearly pure dolomite
end-member samples were studied as were samples containing various
proportions of each.
For the dolomite end-member, porosity was found associated with the
size of the dolomite grains and sorting of grains of quartz, the prin-
ciple insoluble residue. Both a decrease in the size of dolomite
grains and an increase in sorting of quartz grains results in increased
porosity. A comparatively rapid increase in porosity was found beyond
50 to 60 percent quartz content (insoluble residue), which relates to
an increase in the quartz-grain supported framework. For rocks with
more than 50 to 60 percent insoluble residue, the degree of packing
and amount of residue were the two petrographic properties, of the
thirteen measured, which were most strongly associated with porosity
values. Porosity values of core samples ranged from less than 1% for
pure dolomite to nearly 20% for nearly pure sandstone. A greater pro-
portion of the rock beneath the irrigation site is dolomite. An
average porosity value of 5 to 8% might be more typical of the Gates-
burg Formation rocks. Therefore a gravity yield of 31 or higher in
contrast to the 1.5% value computed for the 175 square mile drainage
basin should be more typical for the rocks underlying the irrigation
site. This would vary to some extent depending upon the position of
the water table with respect to individual bedrock units being satur-
ated or dewatered following changes in the water table elevation.
The water table build up in UN-14 and 24 that should have accompanied
two years of recharge at the Agronomy Forestry site (the time required
to approach steady state condition) was computed using selected average
values for the coefficients of storage, gravity yield, and coefficient
of transmissivity obtained from the studies outlined above. Ground-
water recharge was taken as 65,000,000 gallons/year based on precipita-
tion data, potential evapotranspiration computations and the number of
acres irrigated at the Agronomy Forestry site (105). This recharge
amount was assumed based on irrigating 19.5 acres at 2-inches per week
April-November, 18 acres year around at 2-inches per week, 6 acres at
1-inch per week April-November and the high recharge rate of 1,856,000
gallons/acre/year for the 2-lnch per week application amount.
The influence of recharge by reclaimed effluent on local groundwater
levels cannot be measured directly on site for the reasons stated; i.e.,
falling regional water levels due to natural discharge to major springs,
related to prolonged drought conditions, and the superposition of these
declines on water level declines in the area of influence of the
University well field. These regional influences on water levels are
far more pronounced and have masked the effect of water level buildups
in response to spray irrigation.
371
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Allowing for the uncertainty in computing coefficients of storage and
transmissivity for the local aquifer in the vicinity of the University
well field and the Agronomy-Forestry irrigation site, the amount of
water table buildup resulting from recharging 65 million gallons of
water a year may be estimated using Theis (106) nonequilibrium formula
and the law of superposition.
Drawdowns or water level buildups in response to either pumping or
recharge wells may be computed using equation
s = (114.6Q/T) W(u) (3)
Where: W(u) = /Vu/u du = 0.5772 - In u+u - (u2/2.2I)
+ (u3/3.3!) - (u4/4.4!) ...
and u = 2693r2S/Tt ( 4)
•**
>
s = drawdown or buildup in an observation well, in feet
Q = discharge or recharge in a well, in gallons per minute
T = coefficient of transmissivity, in gallons per day/ft
r = distance from pumped or recharged well to the observation well
in feet
S = coefficient of storage, a fraction
t = time since pumping or recharge started, in minutes.
Equation (3) is the nonequilibrium artesian formula introduced by
Theis (106). W(u) is the 'Veil function for nonleaky arltesian aquifers.
Values of W(u) and u that allow for the evaluation of the integral are
given by Wenzel (107) . Equations ( 3 ) and ( 4 ) or modifications of them
were used to compute coefficients for storage and transmissivity ini-
tially given time-drawdowns field data obtained from -various pumping
tests conducted on wells in the University well field and adjacent areas.
Time-drawdown field data curves were matched to the nonleaky artesian
type curve and match point coordinates W(u), 1/u, s, and t were sub-
stituted in equations (3) and (4) to determine aquifer coefficients.
Given estimated average values of these coefficients obtained by the
pumping test method, gravity yield values obtained by the groundwater
depletion method, and porosity values obtained by core analysis, equa-
tions (3) and (4) were again used to compute the water level buildup,
s, that would result at wells UN-14 and UN-24 following two years of
recharge. Recharge amounts computed in gallons per acre per year using
the Blaney Griddle or Thornthwaite method were distributed evenly among
26 assumed wells spaced throughout the irrigated areas and were
expressed in gallons per minute, Q. The distance r, ,in feet was
measured between each assumed recharge well and UN-14-'and UN-24. Equa-
tions ( 3) and ( 4) were solved 26 separate times using a computer
solution devised for the purpose and the water level buildup from each
372
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assumed recharge well was added to the buildup caused by each of the
other 25 recharge wells. The law of superposition allows the buildup
of all 26 wells to be added at any observation well location to give
the total buildup in feet. This gives the total water level rise that
should result in response to recharge of reclaimed effluent and pre-
cipitation at the'irrigation sites. To determine the actual change in
groundwater levelsjin the region, this buildup must be added to ground-
water level declines in response to natural groundwater discharge and
recharge, and declines due to groundwater pumpage which requires a
regional analysis of the entire groundwater system. This analysis was
not conducted for the purposes of this study but it is clear that due
to the small acreage irrigated regional effects will dominate. This
is revealed by the continued water level declines observed in wells
F-3, 23, UN-14, 24 and 17, SC-5 and 18 and other observation wells in
the region despite the recharge derived from the irrigation project.
Computed water level rises in response to spray irrigation shown in
Table 163 must be considered as approximate because the carbonate
aquifer beneath and adjacent to the irrigation site is less than
homogeneous and isotropic as assumed by the Theis theory. However,
computed buildups are probably the correct order of magnitude.
In case one, coefficients of transmissivity and storage were assumed
to be 40,000 gpd/ft and 0.03. Under these conditions, a buildup of
approximately 2.02 feet was computed for UN-14 which was 1300 feet
from the recharge site and 1.7 feet at UN-24 which was 2200 feet away.
If recharge were increased by 50% during wetter years a water table
buildup due to irrigation may have approached 3.0 feet at UN-14 and
2.6 feet at UN-24. Any actual significant decrease in either the co-
efficient of storage or transmissivity values, an entirely plausable
condition, would result in a greater buildup in water levels in
response to irrigation. For example, the same coefficient of trans-
missivity (40,000 gpd/ft), 65,000,000 gallons of recharge per year,
and an average coefficient of storage of .0006 as determined from
pumping tests conducted in the well field would have resulted in 3.4
feet of rise in UN-14 and 3.1 feet in UN-24.
Also, some of the pumping test data suggest that the average coeffi-
cient of transmissivity of the dolomite to sandy dolomite aquifer
that underlies the Agronomy-Forestry site might be as low as 20,000
gpd/ft. Even lower values were measured for less productive blocks of
bedrock that may vary from 5 to 20 acres in area. Flowing fine-to
medium-grained sand and silt are common in most voids in the bedrock
within the upper 100 to 300 feet of landsurface. Cavity fill deposits
would further reduce the storage and transmission properties of these
rocks compared to what might be expected for dolomite bedrock in
nearby areas.
373
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An average coefficient of transmissivity of 24,000 gallons per day/ft
was determined for the Gatesburg aquifer using one pumping well (UN-2)
and six nearby observation wells (Table 162). Even lower average
values of 3,660 gpd/ft itfere determined from other tests. It is
entirely possible that bulk transmission characteristics of these rocks
considering both high avenues of permeability and blocks of poorly
productive rock could be as low as 20,000 gpd/ft. This combined with
a possible average coefficient of storage value as low as .0006 and a
6.5 x 10? gallons of recharge per year could have caused a potential
buildup of 6.3 feet in UN-14 and 5.7 feet in UN-24 (Table 163).
Table 163. Relation Between Aquifer Hydraulic Properties and Water
Table Buildup for Two University Water Supply Wells
Aquifer Hydraulic Properties
Coefficient of Coefficient Water level1
Transmissivity of Storage Buildup-fti/
gpd/ft UN-14 UN-24
40,000
20,000
0.03
0.0006
0.03
0.0006
2.0
3.4
3.6
6.3
1.7
3.1
2.9
5.7
— Based on a computed recharge of 6.5 x 10' gallons/year and an
accumulation time of 2 years.
Pumping tests conducted on wells drilled in Upper Sandy Member of the
Gatesburg Formation that underlies the Gamelands site indicate that
coefficients of transmissivity may approach 422,000 gpd/ft for the
more productive portions of the aquifer (108). No attempt was made to
compute water level buildups in this area due to the present small
scale nature of the existing irrigation project at that site and the
high coefficient of transmissivity values noted for these more perme-
able strata. Recharge effects would be obscured within this ground-
water flow system because the Gamelands site is located above bedrock
which serves to collect and drain groundwater along a zone of high
permeability controlled by zones of fracture, thrust faults, bedding
plane partings and sandstone and sandy dolomite strata that tend to
have significant intergranular permeability. These sandy beds together
with structural complexity facilitate groundwater flow, and localize
solution cavities. A regional groundwater drain or low was apparent
in 1963 within this area that parallelled bedrock strike or the out-
crop trend of the Upper Sandy Dolomite Member (Figure 4). By 1965
374
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this water table low became more pronounced (Fig. 5). By .April of 1970
this drain extended for a distance of 10 miles beyond major springs on
Spring Creek.
Benefits of Recharge
The test plots were selected with a number of factors in mind including
the potential benefits that might accrue from increasing groundwater
recharge. Wells within the principal Pennsylvania State University
well field are located within 450 to 3000 feet of the Agronomy-Forestry
test plots. Nearly 3.5 million gallons of groundwater a day are with-
drawn from wells in this field and two wells located on campus. Water
levels have continued to decline in response to increased pumping
during the 1950's and 60's. Three new wells were added in the field
since 1962 (UN-14, 24, and 26) and deeper pump settings are being
used in these wells, water levels also declined under the influence of
a prolonged drought (1962-1967) when nearly a 50 inch rainfall deficit
was recorded (Fig. 117). During this period groundwater levels
declined more than 80 feet within one of the major aquifers (Gatesburg
Aquifer) in the region, largely due to the influence of the drought
and continued groundwater discharge to major springs that were asso-
ciated with this aquifer.
Water level declines during the period caused a reduction in yield of
UN-17 and UN-24 (Fig. 118). UN-16 was abandoned due to its decline
in productivity. Predicting the loss in yield that is likely to
result in response to water level declines is a particularly difficult
problem where fracture and solution void permeability predominates
within an aquifer (108). This is especially true for the carbonate
aquifers in the vicinity of the irrigation project where solution
voids localized by bedding plane partings, joints, zones of fracture
concentration and individual bedrock units account for most of the
water obtained from wells. A decline in the water table of but a few
feet can dewater one or more major water yielding openings with the
result that the well may be rendered useless or experience a drastic
loss in yield despite the fact that several hundred feet of water may
still be standing in the well. This point is illustrated in Figure 118
for UN-24. This well yielded 450 gallons per minute when it was first
drilled and the static and pumping water levels were at an elevation
of approximately 975 and 920 feet. The yield declined to 100 gpm when
the static and pumping levels fell to 940 and 690 feet. The relation-
ship between water level and yield is not as clearly defined for UN-17.
Significant increases in groundwater recharge in the vicinity of this
well field resulting in a stabilization of or rise in the water table
will have beneficial effects. A new well (UN-26) was drilled in the
area to take advantage of existing pipelines, powerlines, chlorination
facilities etc. with the benefit that more water was obtained at a
375
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a RAINFALL DEFICIT
WATER LEVEL DECLINE
JAN JAN JAN JAN JAN JAN JAN JAN JAN JAN JAN JAN JAN
(1961) (1962! (1963) (1964) (1965) (1966) (1967) (1968) (1969) (1970) (1971)
MONTH AND YEAR
Figure 117. Rainfall Deficit and Water Level Decline Within the Gatesburg Aquifer Due to
Natural Depletion.
-------
JAN
(1964)
JAN
(1965)
JAN
(1966)
JAN
UJ
_i
UJ
UJ
990
970
950
930
910
890
870
850
830
810
UN-24
^-^'
-PUMPING LEVEL
Vx
(1967)
JAN
(1968)
i i i i i i i i i i i i i i i i i i i i i i i i i i t i i i i i i i i i i—i i i i—n—i
NONPUMPING LEVEL
i i i i i i i
900
800
700
600
400
300
200
o
JAN JAN JAN
(1965) (1966) (1968)
JAN
100
Figure 118, Pumping and Non-Pumping Water Levels Related to Decline in Well Yields Within the
University Well Field.
-------
lower cost than for the case if a more remote new well or well field
had to be constructed. UN-26 has had a sustained capacity in excess
of 1,000 gpm since it was placed into service in 1967.
Economies are also involved when production wells can be closely spaced.
The cost of groundwater increases, among other factors, as the number
of wells required to deliver a fixed volume of water increases, as
pumping lift costs increase and as the spacing of supply wells increase.
Theis (106) for example, showed that the optimum well spacing in the
simple case of two wells pumping at the same rate from a thick and
areally extensive aquifer might be approximated by:
YS = 2.4x 108 CpQd/ KT (5)
Where:
Y = optimum well spacing, in feet
Cp = cost to raise a gallon of water 1 foot, consisting
largely of power charges, but also properly including
some additional charges on equipment, in dollars.
R = capitalized cost for maintenance, depreciation, original
cost of pipeline, etc., in dollars per year per foot of
intervening distance between production wells
Qd = pumping or disposal rate in gallons per day
T = coefficient of transmissivity in gallons per day per
foot
A new well field to serve the Borough of State College (Water) Authority
is being planned adjacent to the Gamelands irrigation site where an
expanded 4.0 mgd irrigation system is being planned and designed. It
is hoped that a 1 billion gallon a year or higher capacity well field
can be developed in that area to take advantage of the more than 1
billion gallons of increased recharge expected from the expanded irri-
gation system.
Aside from helping to stabilize pumping levels, the increased recharge
should decrease pumping lift costs within wells in the University well
field and within the proposed State College well field.
Ackerman (109) has shown that the cost of pumping groundwater at any
desired rate for a time period of an hour, day, week, 30-day month and
365-day year can be determined given the rate of pumping in gpm, the
cost of electric energy in $/kw-hr, the total pumping head in ft, and
the wire-to-water efficiency in percent given the following time factor
constants:
378
-------
Time factor Constants
hour 6 x 10
-------
o
o
o
CL
O
1.5
1.0
0.9
0.8
0.7
S 0.6
§ 0.5
UJ
cr
- 0.4
0.3
20
i I I I I I T
PUMPING HEAD 100 FT.
-hr = 3l.40083/Ert
40
60
80 100
WIRE-TO-WATER EFFICIENCY (E0)
IN PERCENT
Figure 119. Power Requirements for Pimping 1000 Gallons of Water
Per Minute at a iOOvfoot Heacl for Various Wire to
Water Efficiencies (109).
380
-------
Expressed another way, the annual cost of lifting 1 mgd 200 feet
assuming a 50 percent wire-to-water efficiency and a power flat rate
of 8 mills per kilowatt-hour would be $3,950. A 100 foot buildup in
the water table could reduce the pumping costs to $1,975 per year for
a 1 mgd well. If the water table were raised 100 ft a 4.0 mgd irriga-
tion system located in close proximity to a well field such as the
University well field could reap a $7,900 annual savings in pumping
costs alone for a single 1 mgd well and up to $31,600 per year for a
four well 4.0 mgd system.
381
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SECTION IX
DESIGN AND COST OF SPRAY IRRIGATION WASTEWATER
DISPOSAL SYSTEM
The purpose of this section is to review and suranarize the various
parameters affecting the design of a spray irrigation wastewater
disposal system and on this basis to determine the annual cost of the
system to the individuals residing in the community in terms of sewer
service charges.
GENERAL CONSIDERATIONS
Distribution System
The distribution system is that portion of the spray irrigation scheme
which actually delivers the water to the land. It consists of physical
units such as headers, laterals, risers, sprinklers, and miscellaneous
fittings. Its design necessitates the use of variables not normally
used in wastewater treatment plant design. The following paragraphs
describe the physical units, variables, and parameters which are asso-
ciated with the design of a wastewater distribution system.
Units. The land on which the distribution system is located is a vital
part of a spray irrigation scheme. Its physical and chemical character-
istics affect many of the parameters used in the design and sizing of
the units. The total land area to be irrigated is divided into a
number of small plots, only a portion of which is under irrigation at
any one time.
The wastewater is distributed on the land by means of a piping system
consisting of sprinklers, risers, laterals, and headers. The sprink-
lers must be chosen, spaced and operated to provide uniform loading on
all areas to utilize the total surface and obtain maximun renovation.
In order to allow an even distribution over a greater area, the sprink-
lers are attached to risers which elevate the sprinklers above thick
vegetative ground cover. The risers are attached to laterals which
constitute the greatest length of pipeline involved in the distribu-
tion system as there usually are several such lines on each header.
Variables. In designing a spray irrigation system for a specific daily
flow from a wastewater treatment plant, four variables must be con-
sidered. These are weekly loading depth, hourly application rate,
nozzle spacing and nozzle operating pressure. Each of these variables
are independent, however, they are closely associated as described
below and in the following section titled Parameters.
383
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The weekly loading depth determines the overall size of the distribu-
tion system. The loading depth usually is expressed in inches of
wastewater applied uniformly over the entire disposal area each week.
For a plant outflow of 0.5 MGD, 64.5 acres are required if the loading
depth per week is 2 inches, whereas, if the loading depth is only 1
inch per week, 129 acres will be needed.
The hourly application rate, expressed in inches per hour, determines
the size of plot that can be irrigated at any one time. Thus, for a
0.5 MGD system if the application rate is 1/4 inch .per hour, approxi-
mately 3.1 acres will be irrigated at any one time, while if the
application rate is only 1/6 inch per hour 4.6 acres will be required
each time.
After the application rate has been determined, the choice of nozzle
spacing establishes the number of sprinklers which will be operating
at any one time. Let us consider the 1/4 inch per hour application
rate which requires a 3.1 acres area. If we choose a 60' x 80' spac-
ing, 28 sprinklers are needed to cover 3.1 acres. Had we chosen a
40' x 60' or a 80' x 100' spacing, 56 or 17 sprinklers would have been
required.
The fourth and last variable is the operating pressure of the nozzles.
With a particular nozzle the greater the pressure the farther the water
will travel and the greater will be the emission rate, therefore the
greater can be the spacing between sprinklers. Since the choice of
pressure is affected so greatly by a number of parameters, it will be
discussed more fully at the end of the following section.
Parameters. This section discusses some of the factors which must be
considered in designing a spray irrigation system for a specific daily
flow from a wastewater treatment plant.
The choice of weekly loading depth depends upon the renovation and
hydrologic capabilities of the site relative to the quality of the
liquid wastes applied. Most of tjie work using domestic municipal
liquid wastes at Perm State was with an application of 2 inches per
week. Very good renovation results were attained under agriculturally
cropped areas at this loading with up to 100 inches per year. Certain
industrial and cannery liquid wastes containing mostly organic parti-
cles may be applied at a much higher amount per week or per year and
adequate renovation attained. Some industrial wastes, however, will
require pretreatment to remove heavy metals and reduce certain salt
concentrations before any may be irrigated.
The hydrologic capabilities of a site must be considered independently
from the site's renovation ability. While sandy surface soils will
permit high rates of application, the amount one can apply may be
diminished by underlying tighter layers. Some of these soils can'be
384
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drained to receive high loadings of liquid wastes while others cannot.
Heavier soils covered with thick stands of vigorously growing hay crops
may accept large amounts of water during the summer months, but may
produce excessive runoff in early spring or late fall at these load-
ings. Effects of geology on the hydrologic regime of irrigated liquid
wastes must be evaluated carefully.
An application rate of 1/4 inch per hour was used for most of Penn
State's systems during the first five years. Most of the present sys-
tem has been converted to 1/6 inch per hour. This lower application
rate is preferable since one often must irrigate during and after
heavy rains. Additional factors which affect the rate of application
include: the soil texture, structure, and permeability; the soil
cover crop and management procedures; the surface topography; and the
climatic conditions.
The choice of spacing between sprinklers is associated closely with
both the application rate and the amount of pressure at the nozzle.
The primary factor which affects the choice of spacing is the vegeta-
tive cover -- open field crops or woods. As discussed under Irrigation
Application Systems in Section IV on Methods and Materials for Penn
State's solid-set system, an 80' x 100' spacing was preferred for open
fields and a 60' x 80' spacing was recommended for wooded areas.
The prevailing direction and intensity of winds affect the uniformity
of application, particularly at the wider sprinkler spacings. As the
spacing is increased, the height of the spray stream must be increased
according to the laws of projectile motion. As the top of the spray
stream arc becomes higher the wind has a greater distorting effect on
the distribution pattern. Thus, wind breaks often become an integral
part of the irrigation distribution system design.
The nozzle pressure and diameter are chosen such that the appropriate
rate of application can be distributed uniformly over the specified
spacing between sprinklers. A pressure of 48 psi will cause 8.3 gpm
to flow from a 13/64 inch diameter nozzle. This would be appropriate
for a 1/6 inch per hour application rate on a 60' x 80' spacing. For
a spacing of 80' x 100' and an application rate of 1/6 inch per hour,
58 psi applied to a 1/4 inch diameter nozzle would give 14 gpm which
is an appropriate design.
While the above discussion of application rate, nozzle spacing, and
nozzle operating pressure is appropriate for the design of a solid-set
irrigation system; it is not adequate for the designs of other irriga-
tion systems as: the center pivot, the giant gun, the traveling gun,
and various other self-propelled or hand moved systems. Frequently
one of the above type systems is just as appropriate as the solid-set
system and usually is much more economical. In most of Pennsylvania,
however, the geology, topography, and tree cover encourage the use of
solid-set systems. The solid-set arrangement is the only one discussed
in this report.
385
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The physical features of the land, in addition to affecting the vari-
ables, also directly affect the design and cost of the entire system.
The total head requirement for the system is directly dependent upon
the difference in elevation between the pumping plant and the distri-
bution areas; as well as the friction loss in the transmission and
distribution lines, and the pressure requirements of the sprinkler
heads.
Design for a rough, undulating terrain, of course, is more complicated
than for a gently sloping area because of static head changes and more
importantly the need for draining all lines during periods of freezing
conditions. The rougher the terrain the more difficult this becomes.
The number of drain locations should be kept to a minimum to reduce
labor and to permit more efficient management.
The configuration of the field frequently is determined by the avail-
ability of land. Excess lengths of pipe and inefficient distribution
system arrangements often are required due to unavailability of large,
contiguous areas.
The variations inherent in the variables and parameters are exceedingly
great. Thus, to present a generalized design which applies to all
situations would present an almost insolvable problem. The cost
analyses in this report is for one particular design. Costs for other
designs may be computed from graphs and nomographs in Allender's thesis
(110). In presenting design procedures in subsequent sections of this
report, an attempt will be made to use representative limits but these
limits must be reviewed with the preceding discussion in mind.
Transmission System
The transmission system which delivers the water to the distribution
system, includes the remaining facilities involved in the spray irriga-
tion scheme. The individual unit's design for the transmission system
is dependent mostly on the waste's physical and chemical characteris-
tics. The procedures commonly are encountered in the design of more
conventional treatment schemes. The units usually involved are:
screens, a flow equalization tank or lagoon, pumps, pipeline and a
centralized control system. These units are required in nearly all
systems and are further defined in the following paragraphs.
Units. A control system will have to be provided for the wastewater
pumps. This system will be quite simple if no control over the sprink-
ler system is needed, but, as the desired automation of the sprinkler
system increases, the required control system becomes more complex.
Automation of the sprayfield can vary from automatic or remote valve
operation to a completely automated system. This latter system could
involve such items as pressure indicators, devices to allow drainage
of individual lines and automatic control of valves to allow irrigation
386
-------
fields to be placed in or out of operation. Even further automation
could allow an automatic tabulation of fields irrigated and could
provide a sequence to prevent irrigation of a single field more than
once per week.
Any wastewater effluent contains suspended "solids. The size of these
solids and the frequency with which they are encountered are a func-
tion of the efficiency of the treatment plant. These solids, which
are not normally considered an effluent disposal problem, can cause
clogging of the nozzle orifices and must be removed. This removal is
accomplished most easily by use of screens which can be cleaned
continuously.
As implied previously, the number of acres to be irrigated each time
and the application rate establish the instantaneous flow rate to the
distribution system. Thus, if separate pumping facilities for peak
loads are not desired, any variation in the effluent flow over a year's
time must be distributed over this time period to allow an even flow
rate to the fields. This even distribution can be accomplished only
by means of an equalization tank or lagoon which allows the waste to
be stored at times of excess flow until times of minimum flow.
Delivery of the waste effluent to the distribution field must be at a
guaranteed pressure. Thus, pumps capable of delivering the desired
flow at the desired distribution field pressure must be provided.
Pump discharge pressure also must be sufficient to overcome static
differences in elevation, plus pipeline losses.
The transmission pipeline is, of course, a force main discharging from
the pumping station and should be designed as such.
As in the distribution system, the transmission system units are
affected by items which will be considered as both variables and
parameters.
Variables. The only true variable is the transmission pipeline diame-
ter!Diameter variation will affect both the cost of the pipeline and
the pump discharge head. The pipeline cost is a direct function of
it's diameter while the pump size and power requirements are an inverse
function of the pipe diameter.
The sprinkler nozzle size like the operating pressure, most likely
will be determined in the distribution system design. However, it
determines the screen hole size or vice versa as the screen must be
slightly smaller than the nozzle size.
Parameters. The type and size of the units within the transmission
system are determined mainly by the parameters; effluent solids, flow
characteristics, sprayfield elevation and location, and soil type. All
387
-------
the parameters will differ from one installation to another but once
determined for an individual area they will remain fairly constant.
SYSTEM DESIGN
In order to estimate the cost of a spray irrigation system, it is
first necessary to make a preliminary design of the system. As each
system must be designed individually, the preliminary design informa-
tion cannot cover all situations and the final design should be done
by a competent engineer. However, this information will serve to
provide a design sufficiently detailed so that an accurate preliminary
estimate of costs can be made. This preliminary design information
will be presented in two parts: the distribution system and the
transmission system.
Distribution System
In designing the distribution system the following items must be
determined: the number and type of sprinklers, the number of risers
and unions, the length, size, and number of laterals, the length and
size of the header, and the number of valves. Since these items will
be similar over the entire area of the distribution field, the methods
presented will give the required number and lengths of these items
per acre.
The actual graphs, tables, and nomographs used in the calculations, as
well as explanations of their use are described in Allender (110).
The system is developed from the sprinkler spacing as the first vari-
able. The parameters affecting this variable have been discussed
previously and it is necessary now only to set the upper limits for
the spacing. Maximum spacing between laterals of approximately 80 feet
in woodlands provide satisfactory distribution of effluent at reason-
able costs when using solid-set systems. Since the number and size of
the other distribution system units are both inversely and directly
proportional to this variable, an optimum value at which costs will be
a minimum should exist for open fields where larger spacings can be
used. This relationship will be discussed at greater length in a later
section.
The operating pressure and application rate must also be determined
prior to the distribution system design. Operating pressure has both
lower and upper limits which are determined by the nozzle selected.
The lower limit is set by the minimum pressure necessary to operate
the sprinklers and adequately cover the spacing. This value differs
according to the sprinkler chosen but in most cases it will be between
40 § 50 psi for a 60' x 80' spacing. The upper limit, likewise, is
determined by the sprinkler type and is limited by the point at which
388
-------
an. even distribution is no longer possible. Pressures in the range of
50-65 psi ordinarily are used for a spacing of 80' x 100'.
The permissible application rate will differ according to the physical
parameters existing in any one area. In the Penn State study appli-
cation rates of 1/6 and 1/4 inch per hour were used. The hourly
application rates were chosen sufficiently low to insure infiltration
even if heavy soil and wet conditions are encountered.
Work at Penn State indicated that with a weekly application depth of
four inches excessive quantities of some of the waste constituents
were found in the water after it had passed through the soil. In a
poll of seven industries in Pennsylvania using spray irrigation (111),
three industries using loading depths between 21 and 37 inches per week
either reported a runoff problem or allowed runoff and discharge. The
four industries reporting no runoff problems were using application
depths within the 2 inch per week limit of the Penn State study and it
is believed that this limit is a fairly reasonable value. Most of the
figures presented in Allender (110) are thus based on these values but
some latitude was allowed for choice of other values.
A loading amount of two inches per week and an application rate of
1/6 inch per hour were chosen as preferred values under Penn State
conditions. These satisfied the physical parameters and required a
reasonable amount of labor to operate the system. For instance, at
1/6 inch per hour and two inches per week the irrigation system need
be changed only once every 12 hours while at 1/4 inch per hour the
irrigation plots must be rotated every eight hours.
After compatible nozzle spacings, operating pressure, and application
rate have been established, the remainder of the distribution system
can be designed.
The amount of land needed for the irrigation field is a major item and
should be the first concern. The number of acres necessary can be
found from the daily flow and the weekly application rate using Figure
120. Enter with the weekly loading depth, 2 in/wk (Pole A) and the
daily flow, 1 mgd (Pole B) and read the area requirement where the
resulting line intersects Pole C. To obtain the total cost pivot on
Pole C to the cost/acre (Pole D) and read the total cost where the
resulting line intersects Pole E.
It is necessary to have the spacing less than the effective distribution
diameter to allow overlapping of the streams and give an even applica-
tion. Several spacing arrangements and procedures are illustrated in
Figure 121 and the relation between effective distribution diameter and
required sprinkler spacing is given in Figure 122. The miriber of sprink-
lers and risers needed per acre is a function only of the type spacing
and can be determined by use of Figure 123.
389
-------
1 ' 1
3 O
9 O
9 OS
1 1
O
O
CO
1 1
o
o
1 1
§
SO
1 1
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o
m
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8
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o
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auoz aajjnq q»pi 3003
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o
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I i
Figure 120, Land Requirements and Costs with: and without a Buffer
Zone Related to Daily Flow and Application Rates.
390-
-------
'pi
Square Spacing
0.6(d) S 2 - 0.6(d)
-------
I
Pi
W fl)
VO M
tsJ ^
P2 —H
Triangular or Intermittant Spacing
Spl - 0.65(d) Sp2 - 0.75(d)
-------
140
120
7100
a
H
55
C
CO
80
60
H
O
W
Cb
Pa
U
40
20
Square
Rectangular
Triangular
i
20
40 60
SPACING (ft.)
80
100
Figure 122, Required Sprinkler Separation Distances in Relation to
Effective Distribution Diameter with Three Types of
Spacing.
393
-------
w
PM
en
PC
w
en
Pi
w
50
Type Spacing:
Square
Rectangular
Triangular
70 90 110 130
EFFECTIVE DISTRIBUTION DIAMETER (ft.)
150
Figure 123. Number of Sprinklers per Acre in Relation to Effective
Distribution Diameter with Three Types of Spacing.
394
-------
Once the number of sprinklers to be used are determined, the type of
sprinkler can be chosen. Each manufacturer has several models avail-
able and each model can be varied by changing the nozzle orifice size
or the inclination of the nozzle with the horizontal. Tables are
usually presented by the manufacturer vMch give the effective distri-
bution diameter and the individual sprinkler discharge as a function
of the operating pressure and the nozzle hole size for each model.
The model, nozzle hole size, and operating pressure must be determined
by use of the effective distribution diameter and the nozzle flow.
The nozzle flow can be obtained from Figures 124 and!25 for 1/4 and 1/6
inch per hour application rates. Figure 126 allows the reader to
convert that result to a discharge rate for any other hourly applica-
tion rate.
The length of lateral pipeline required is a function of the spacing
and the sprinkler configuration scheme and can be found for one acre
by use of Figure 127. This figure again uses effective distribution
diameter instead of spacing distance so that differences due to the
positioning of the sprinklers can be shown.
After the length of pipeline is deteimined, its diameter can be deter-
mined from the allowable headless in the field. A pressure difference
between the ends of a lateral of no greater than 20% of the maximum
operating pressure frequently is recommended. This 20% pressure vari-
ation produces only a 10% volume variation which is quite acceptable.
Since pressure change is realized as both static (elevation) changes
and friction losses, not all of the pressure difference can be assigned
to friction loss within the header and laterals. Pressure changes due
to elevation differences must be deteimined prior to assigning an
allowable headloss to the laterals and header. The headloss in the
header should be assigned first and will be discussed later. Since
all laterals are assumed to have equal flow only one lateral need be
considered in determining the allowable diameter. The lateral flow
can be obtained from Figure 128 and the individual lateral length can be
obtained from Figure 129. Figure 130 is a nomograph from which the
allowable pipe diameter can be obtained.
Figure 128 assumes the total flow will be applied to one irrigation plot
at any particular time. If more than one plot is used, the flow given
by the nomograph will have to be divided by the appropriate number.
The nomograph is used as follows: enter with the daily flow (Pole A)
and the hourly application rate (Pole B); pivot on Pole C to the proper
side dimension ratio, the ratio of the field dimension perpendicular
to the laterals (width) to the field length (Pole D); and read the
lateral flow where the resulting line intersects Pole G.
Figure 129 also assumes that only one plot will be used at any one time
and if more are used the lengths will have to be reduced accordingly.
The nomograph is used as follows: enter with the daily flow (Pole A)
395
-------
30 r-
s
ex
00
CO
i—i
Q
f*i
W
M
03
PU
CO
§
a
ss
M
25
0
Figure 124.
Square
Rectangular
1 1
60 80
l
100
1
120
Lai.
1
140
EFFECTIVE DISTRIBUTION DIAMETER (ft.)
Sprinkler Discharge for Various Effective Distribution
Diameters and a 1/4 Inch per Hour Application Rate.
396
-------
25 r-
w
o
o
C/3
1-1
a
w
M
P-l
53
t>
o
M
>
20
Type Spacing:
• Square
•Rectangular
•Triangular
80
100
120
140
EFFECTIVE DISTRIBUTION DIAMETER (ft.)
Figure. 125. Sprinkler Discharge? for Various Effective Distribution
Diameters and a 1/6 Inch per Hour Application Rate.
397
-------
00
6
o-
60
CM
I
400
300
200
100
0
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1500-
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loooh
750-
500
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4
j__ Type Spacing;
I •"• """ "Square
, .^»__ __ — . — —Rectangular
1 i i i i i i
0 60 ' 80 100
^ ^x.
1 1 i
120 140
EFFECTIVE DISTRIBUTION DIAMETER (ft.)
Figure 127. Required Lengths of Lateral Pipeline for Various
Effective Distribution Diameters.
399
-------
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o
10
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Figure 128. Lateral Flow in. Relation to Daily Flow, Application Rate and Side Dimension Ratio
of the Irrigation Plot.
-------
_ 10
- 6
- 4
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-.8 g
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Figure 129. Required Lengths of Lateral Pipeline in Relation to Daily Flow, Application Rate
and Side Dimension Ratio of the Irrigation Plot.
-------
and the hourly application rate (Pole B); pivot on Pole C to the proper
side dimension ratio (Pole D) and read the lateral or header length
where the resulting line intersects Pole G.
The header length, like the individual lateral length, can also be
determined from Figure 129. The diameter of the header can then be
determined in the same manner as that for the lateral. Its value and
the length of line to be sized will depend on the point at which the
water is introduced to the header. In most cases it should be at the
one-half point to allow only one half the total flow in any one length
of pipe at any one time.
Figure 130 allows the appropriate pipe diameter to be found using the
pipeline flows and lengths found in Figures 128 and 129, the sprinkler
operating pressure, and the allowable headless. This nomograph is
used by entering with the pipeline lateral or header flow (Pole A) and
the pipeline length (Pole B); pivoting on Pole C to the operating
pressure (Pole D); pivoting again on Pole E to the proper percentage
(Pole F) and reading the diameter from Pole G. The right side of this
pole is to be used for flows between 0.1 cfs and 10 cfs while the left
side is to be used for flows between 10 cfs and 1000 cfs. Flows less
than 0.1 cfs are not presented as even under maximum conditions the
required diameter would not exceed four inches.
Once the> number, length and size of units are determined for an acre,
the total numbers and lengths can be found by multiplying by the total
number of acres required for the entire system. The total number of
acres required can be found by use of Figure 120. This nomograph was
constructed for determining land costs but the area in acres is avail-
able as an intermediate value. There will be little if any variation
in the land requirement for identical average daily flows. Even in
systems where some of the effluent can be sold to outsiders for irriga-
tion purposes, an area equal to that determined above will be required.
Sufficient area must be provided for seasons during which there is
little or no irrigation sale.
Transmission System
For a preliminary design of- the transmission system it is necessary
only to determine the headloss in the transmission line, its diameter,
and the capacity of the equalization lagoon and pumps.
The headloss in the transmission line can be determined in two ways:
first by assigning a specific headloss to the pipeline and using
Figure 131 to determine the pipe diameter or by choosing a pipe diameter
and finding the headloss from Figure 131. This last figure gives the
headloss per 100 feet for different flows and pipe sizes. Either of
the above methods allows for optimization of one of the two major cost
items (power costs and pipeline costs) but neither considers both.
402
-------
H
I
r 10 10000 _ 1
400 jr
300 '_
200 _
•
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-------
Note:
Numerals denote pipe
diameter in inches
FLOW (cfs)
Figure 131. Headloss for Various Flows and Pipe Diameters.
-------
Under the section discussing costs, presented later, both will be con-
sidered and an optimum pipe size determined for the various flows.
This pipe size can then be used along with Figure 131 to determine the
expected headloss.
To balance the normal flow variations experienced in each individual
sewerage collection system against the daily pumping capacity several
alternatives may be employed. One of these would be to provide an
equalization lagoon with a capacity large enough to store the excess
flows above a uniform daily pumping capacity over a time period long
enough to be counter balanced in total mass by the deficiencies in
flow below that uniform daily pumping capacity. This time period was
computed in 1968 for six sewerage systems in Northwestern Pennsylvania
and is expressed in Table 164 in terms of storage needs as a percent
of the average daily flows. The values ranged from 17001 to 6400% with
an average of 40001. The latter value was used and it was assumed that
a storage lagoon with a capacity equal to 40 times the average daily
flow must be provided.
Table 164. Effluent Storage Needs.
Item A
Average Daily
Flow (MGD) .291
Storage Needs
(% of Average
Daily Flow) 5500
B
.447
3100
C
.533
3900
D
1.035
6400
E
1.205
3800
F
2.60
1700
A substantial reduction in the size of the equalization lagoon may be
possible by utilizing the inherent range in pumping capacity of any
pump and by balancing temporary increased loads on a particular portion
of the irrigation site with equivalent decreased loads at some other
time.
If an equalization lagoon is not provided, the transmission and distri-
bution system must be sized to handle the weekly variations in flow if
the irrigation cycle is a weekly one. Such a system may have to include
additional land for irrigation or allow for temporary increased loading
during periods of high flow, pumps with controllable variable speed or
a standby supplemental pump to provide increased capacity, an oversized
transmission line, and more intensive management.
405
-------
SYSTEM COSTS
The net cost of effluent disposal by spray irrigation is dependent upon
the system required to do a specific job, at a specific location, at a
specific time, as well as the procedures adopted for management of the
spray field. Since different situations require different designs and
management procedures, no general overall cost information can be given.
Based on certain assumptions used by Allender (110) the estimated cost
of hypothetical systems carrying flows of one, five and ten million
gallons per day (MGD) will be presented. The assumptions may or may
not fit another specific situation but they will serve as a basis for
a rough cost estimate under what can be regarded as moderate parameter
levels. The costs will be discussed under the general areas of capital
costs of the pumping system and delivery system, and operation costs.
Engineering and contingency costs were estimated at approximately 10%
of other capital costs and maintenance and contingency costs at approx-
imately 10% of annual operating costs.
Pumping System
It is assumed that the system will be pumping secondary treatment
municipal wastewater and that an equalizing storage pond with a capa-
city forty times the average daily flow will be needed to insure a
more or less constant pumping rate.
The pumping station is a typical wastewater station with the usual
stand-by pump and discharging into a force main. Also included is a
screening system before the pump station to prevent clogging of the
sprinkler nozzles.
Delivery System
In this computation the delivery system includes a one mile trans-
mission pipeline (force main) and the spray field itself, including
land and the distribution system of sub-mains, laterals, sprinklers
and fittings.
The estimates include the purchase of land at $140 per acre, the aver-
age cost of land in 1964 in counties in Pennsylvania with less than 5%
urbanization. In counties with more than 101 urbanization the average
cost was $680 per acre. The amount of land required is based on a
total application of two inches per week at an application rate of one-
sixth inch per hour. The land is assumed to be open fields rather than
forest. Land survey and site preparation costs are also included.
The force main is one mile long with a 200 ft elevation lift. This
distance is probably short for many larger installations, but may be
quite appropriate for the small system where this process may have its
widest application.
406
-------
The sprinkler system uses solid set aluminum piping with 140 foot
effective distribution diameter sprinkler heads placed in a rectan-
gular spacing of 98 ft by 70 ft and with 3-foot risers.
Operation
Operation of the system assumes that the municipality must provide its
own sprayfield which is capable of receiving the entire flow. While
it is realized that this water can be of great benefit to private
agricultural lands, it is felt that continuous, uninterrupted disposal
on these private lands would not be possible. On this basis, sale of
effluent to owners adjacent to the transmission pipeline would be a
definite possibility. Calculations on the returns available from this
sale under climatic conditions similar to those in central Pennsylvania
indicated it would be an insignificant fraction of the total cost and
it has not been included in these estimates.
Labor costs were estimated at $3.00 per hour for semi-skilled labor
. on a basis of manually operated irrigation changes involving one hour
per 60 acres in the spring, summer and fall and two hours per 60 acres
in the winter.
Power costs are computed as the cost required to deliver the effluent
to the field distribution system at zero pressure after a distance of
one mile and an elevation difference of 200 feet and the cost to oper-
ate the field distribution system at a 2-inch per week loading depth
and a 1/6 inch per hour application rate.
Amortization costs were based on a 20-year period at 6% interest.
No detailed economic analysis was made of the profits which might
accrue from operating the disposal area as a crop production area.
An economic analysis of the Muskegon County project (112) indicated
a potential net annual return to the operator for land, risk, manage-
ment and labor ranging from $2.50 to $40.50 per acre from sale of
baled hay and $25 to $75 per acre for lawn sod harvested every other
year. Rental rates of the irrigated land to farmers could net from
$5 to $20 per acre per year depending on the productivity of the site
and value of the crops grown.
On the basis of the selected design parameters and ignoring any agri-
cultural benefits, irrigation sales, recharge benefits or environmental
benefits to the surface waters of a region, the estimated cost for
flows of one, five, and ten MGD are shown in Table 165 in 1967 dollars.
The percent distribution of the costs is also given in the table.
The data indicate that capital cost varies from $439,220 for a one
system to $2,431,280 for a ten mgd system. Annual cost also shown on
Table 165. includes amortization of the capital cost in 20 years at 61
407
-------
Table 165. Costs of a Land Disposal System for Treated Municipal Wastewater (1967 dollars)
-fa.
O
00
Item
Capital Costs
Pumping system:
Pump station, screens
Storage lagoon
Delivery system:
Pipeline - 1 mile
Land, survey, site preparation
Distribution system
Engineering $ Contingencies
Total Capital Cost
Annual Cost
Amortization (20 yr. , 6%)
Labor
1
84,000
123,000
71,500
44,000
66,020
50,700
439,220
36,750
1,900
%
19.1
28.0
16.3
10.0
15.0
11.6
100.0
78.9
4.1
Flow
5
179,000
350,000
132,000
219,000
336,700
152,100
1,369,500
111,100
1,900
- MGD
1
13.1
25.6
9.6
16.0
24.6
11.1
100.0
75.7
1.3
10
258,500
600,000
195,000
440,000
675,380
262,400
2,431,280
197,800
1,900
%
10.6
24.7
8.0
18.1
27.8
10.8
100.0
75.2
0.7
Power - Transmission system -
1 mile + 200 ft elevation 2,310 5.0 11,740 8.0 21,260 8.1
-------
Table 165 * Continued.
Item
Power - Distribution
system - irrigation
Maintenance and Contingencies
Total Annual Cost
Flow - MGD
1 % 5 1 10 %
2,200 4.7 10,800 7.3 21,600 8.2
3,410 7.3 11,300 7.7 20,500 7.8
46,570 100.0 146,840 100.0 263,060 100.0
O
(£>
-------
interest and ranges from $46,570 to $263,060 for the one and ten ragd
flows. Labor would be by personnel also used for other work and is
considered constant in this flow range.
Although the distribution of costs among the various system components
is given in Table 165, they are presented graphically in Figure 132.
In this figure it can be seen that the capital costs are not equally
distributed among the system components. The 40-day storage lagoon is
the largest single cost component ranging from 28% to 24% of the total
capital cost. Since the cost of the transmission pipeline would be
almost directly proportional to length it is obvious that a large
change in length of the pipeline could change the total figures con-
siderably.
Annual wastewater treatment costs are often expressed in terms of cents
per thousand gallons of wastewater treated. Annual cost on this basis
is presented in Figure 133.
The cost shown in Figure 133 compares favorably with other wastewater
treatment costs. With secondary treatment cost at 15 cents per thou-
sand gallons for a 10 mgd plant, sprinkler irrigation would add 7.2<£
per thousand gallons or about 48 percent to the total treatment costs.
Chemical treatment for phosphorus removal is generally estimated at
about 5 cents per thousand gallons, and tertiary treatment by filtra-
tion and activated carbon at 20 cents. Nitrogen removal by denitrifi-
cation would add about 5 cents per thousand gallons. The total cost
for conventional physical-chemical treatment would thus total 30£ as
against 22.2
-------
500
£ 400
o
o
S 300
g
"§ 200
a
a.
o
O
100
—
—
—
—
—
—
Engineering
^/^ntinnAn^iAr
cuiiTiiyBnciBS
Miscellaneous
1 Mile Pipe
Pumping
Station
Lagoon
Distribution
System
Maintenance
contingencies
Power (A)
Power (B)
Labor
A « • * •
Amortization
of pipe
AnY"*"tiyntinn
Of
Distribution
System
(All Capital
costs but
pipeline)
—
_
—
—
_.
50
40
^w k.
o
o
30 |
o
20
10
o
u
"o
c
Capital Annual
Figure 132. Capital and Annual Cost Distribution for a 1 MGD Spray
Irrigation Wastewater Disposal System.
411
-------
18
16
CO
3 l4
C9 12
8
Q 10
8
6
<
ID 4
COST INCLUDES I MILE PIPELINE
PLUS 200 FOOT ELEVATION LIFT
i i i i
468
FLOW-MGD
10
Figure 133. Annual Cost of Spray Irrigation Wastewater Disposal
System per Thousand Gallons for Various Daily Flows.
412
-------
18
16
14
*
I 10
8
a
COST INCLUDES I MILE PIPELINE
PLUS 200 FOOT ELEVATION LIFT
4 6
FLOW-MGD
8
10
Figure 134. Annual Cost of Spray Irrigation Wastewater Disposal
System per Equivalent Dwelling Uhit (EDU) for Various
Daily Flows.
413
-------
SECTION X
ACKNOWLEDGMENTS
Accomplishments of the Waste Water Renovation and Conservation Research
Project have resulted from the cooperation of many persons and agencies
both in and out of the University. The initial phases of the work,
1962-1965, were financed by the Penn State Central Fund for Research
and Agricultural Experiment Station Hatch and State Funds. Several
members of the Pa. Dept. of Health assisted in the initial planning and
preparation of an application for a Sanitary Water Board permit auth-
orizing the study.
On May 1, 1965 a Water Supply and Pollution Control Demonstration Pro-
ject Grant (WPD 95-01-65) was received from the Public Health Service
of the U.S. Dept. of Health, Education and Welfare and subsequent
grants, WPD 95-02, -03 and -04 (EPA-16080DYJ) of successor agencies,
FWPCA and FWQA, U.S.D.I. and EPA, supported the work through 1969.
Support funds were also received through O.W.R.R.-U.S.D.I. Matching
Grant No. 14-01-001-837 for a portion, of the study. At the same time
continuing support was received from the Ag. Exp. Sta. and from the
Office of the Vice-President for Research through the Institute for
Research on Land and Water Resources.
The assistance provided by Mr. Richard E. Thomas, the grant project
officer since Sept. 30, 1970 is particularly acknowledged.
The cooperation of various departments and divisions of the University
is also gratefully acknowledged, notably: the Depts. of Agronomy,
Forest Science, Agricultural Engineering, Geological Sciences and
Civil Engineering and the Divisions of Maintenance and Operation and
Farm Operations.
In addition to the graduate students whose contributions are acknowl-
edged in various citations the contribution of various former and
present research assistants and technicians is also gratefully
acknowledged, notably among these are: Joseph Eichert, Charles Robbins,
Forrest Long and William Haas.
415
-------
SECTION XI
REFERENCES
1. Parizek, R. R., L. T. Kardos, W. E. Sopper, E. A. Myers, D. E.
Davis, M. A. Parrel! and J. B. Nesbitt. Waste Water Renovation
and Conservation. Penn State Studies No. 23. The Pennsylvania
State Univ., University Park, Pa. 71p., 1967
2. Glantz, P. J. and T. M. Jacks. Significance of Escherichia Coli
serotypes in wastewater effluent. J. Water Poll. Contr. Fed.
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3. Caruccio, F. T. The hydrogeology of the sewage disposal experi-
ment area northwest of State College, Pennsylvania. M.S. Thesis,
Dept. of Geology and Geophysics, The Pennsylvania State Univ. 1963
4. Landon, R. A. The geology of the Gatesburg Formation in the
Beliefonte Quadrangle, Pennsylvania and its relationship to
general occurrence and movement of groundwater. M.S. Thesis,
Dept. of Geol. and Geophys., The Pennsylvania State Univ., 1963
5. Lattman, L. H. and R. R. Parizek. Relationship between fracture
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J. Hydrology 2: 73-91. 1964
6. Parizek, R. R. and B. E. Lane. Soil-water sampling using pan and
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within the profile. Soil Sci. 94: 379-386. 1962
8. Edwards, Ivor K. The renovation of sewage plant effluent by the
soil and by agronomic crops. Ph.D. Thesis, Dept. of Agronomy,
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9. Parizek, R. R. Site selection criteria for wastewater disposal -
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10. Givens, F. G., Jr. The development of irrigation sprinkler heads
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417
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11. Brown, C. D. The development of stationary or if ice-rotating
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14. Myers, J. C. . A study of drainage conditions on a hillside receiv-
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24. Henry, C. D., R. E. Nbldenhauer, L. E. Engelbert and E. Truog.
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27. Day, A. D. and T. C. Tucker. Production of small grains pasture
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30. yercher, B. D., et al. Paper mill wastes for crop irrigation and
its effects on the soil. Louisiana State Univ. and Agr. and
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31. Baars, J. K. Principles and Applications in Aquatic Microbiology.
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32. Laverty, F. B. Water spreading operations in the San Gabriel
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34. Stone, R. and W. F. Garber. Sewage reclamation by spreading basin
infiltration. Proc. Am. Soc. Civil Eng. 77: sep. 87, 26 pp. 1951
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infiltration. Trans. Am. Soc. Civil Eng. 117: 1189-1217. 1952
36. Anon. Field investigation of waste water reclamation in relation
to ground water pollution. Calif. Water Poll. Contr. Board Bui. 6.
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37. Sanitary Engineering Research Lab. An investigation of sewage
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38. Greenberg, A. E. and H. B. Gptaas. Reclamation of sewage water.
Am. J. Pub. Health 42: 401-410. 1952
39. U. S. Public Health Service. Drinking water standards. Federal
Register 27: 2152-2155. 1962
40. Greenberg, A. E. and P, H. McGauhey. Chemical changes in sewage
during reclamation by spreading. Soil Sci. 79: 33-39. 1955
41. Greenberg, A. E. and J. F. Thomas. Sewage effluent reclamation
for industrial and agricultural use. Sewage and Industrial
Waste 26: 761-770. 1964
42. KLein, S. A., D. Jenkins and P. H. McGauhey. The fate of ABS in
soils and plants. J. Water Poll. Contr. Fed. 35: 636-654. 1963
43. Robeck, G. G., et al. Degradation of ABS and other organics in
unsaturated soils. J. Water Poll. Contr. Fed. 35: 1225-1236.
1963
44. McKinney, V. N. and J. M. Symons. Bacterial degradation of ABS.
I. Fundamental 'Biochemistry. Sewage and Ind. Wastes 31: 549-
556. 1959
45. Sawyer, C. N. and D. W. Ryckman. Anionic synthetic detergents
and water supply problems. J. Am. Water Works Assoc. 49: 480-
490. 1957
46. NbKee, J. E. and F. C. McMichael. Final report of research of
waste water reclamation at Whittier Narrows. W. M. Keck Lab. of
Environmental Health Engineering, Calif. Inst. of Technology.
224 pp. 1965
47. Pennypacker, S. P., W. E. Sopper and L. T. Kardos. Renovation
of waste water effluent by irrigation of forest land. J. Water
Poll. Contr. Fed. 39: 285-296. 1967
48. Laverty, F. B., R. Stone and L. A. Msyerson. Reclaiming Hyperion
effluent. Proc. Am. Soc. Civil Eng., J. San. Eng. Div. 87: SA6:
40. 1961
49. Scofield, C. S. and F. B. Headley. Quality of irrigation water
in relation to land reclamation. J. Agr. Res. 21: 265-278. 1921
50. Kelley, W. P., S. M. Brown and G. F. Liebig, Jr. Chemical effects
of saline irrigation water on soils. Soil Sci. 49: 95-107. 1940
51. Fraps, G. S. and J. F. Fudge. Replacement of calcium in soils by
sodium from synthetic irrigation water. J. Am. Soc. Agron. 30:
789-796. 1938
420
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52. Wilcox, L. V. The quality of water for irrigation use. U.S.D.A.
Tech. Bui. 962. 1948
53. United States Salinity Laboratory Staff. Diagnosis and improve-
ment of saline and alkali soils. U.S.D.A. Agriculture Handbook
No. 60. L. A. Richards, Editor. 1954.
54. Klausner, S. D. Oxygen relationships in a soil treated with
sewage effluent. M.S. Thesis, Dept. of Agronomy, The Pennsylvania
State Univ. 1968
55. Jardine, J. D. Boron relationships in a soil from a sewage
effluent disposal site. M.S. Thesis, Dept. of Agronomy, The
Pennsylvania State Univ. 1971
56. Hook, J. E. Characterization of phosphorus in soils treated with
sewage effluent. M.S. Thesis, Dept. of Agronomy, The Pennsylvania
State Univ. 1971
57. Hatcher, J. T., C. A. Bower and M. Clark. Adsorption of boron by
soils as influenced by hydroxy-aluminum and surface area. Soil
Sci. 104: 422-426. 1967
58. Cole, C. V., S. R. Olsen and C. 0. Scott. The nature of phosphate
sorption by C&QO-^. Soil Sci. Soc. Am. Proc. 17: 352-356. 1953
59. Hsu, Pa Ho. Adsorption of phosphate by aluminum and iron in soils.
Soil Sci. Soc. Am. Proc. 28: 474-478. 1964
60. Olsen, S. R. and F. S. Watanabe. A method to determine a phos-
phorus adsorption maximum of soils as measured by the Langmuir
isotherm. Soil Sci. Soc. Am. Proc. 21: 144-149. 1957
61. Langmuir, I. The adsorption of gases on plane surfaces of glass,
mica and platinum. J. Am. Chem. Soc. 40: 1361-1402. 1918
62. Davis, L. E. Sorption of phosphates by non-calcareous Hawaiian
soils. Soil Sci. 40: 129-158. 1935
63. Fisher, E. A. The phenomena of adsorption in soils: a criteria
'discussion of the hypothesis put forward. Trans. Faraday Soc.
17: 305-316. 1972
64. Russel, G. C. and P. F. Low. Reaction of phosphate with kaolinite
in dilute solution. Soil Sci. Soc. Am. Proc. 18: 22-25 1954
65. Daniels, F. and R. A. Alberty. Physical Chemistry, second edition.
John Wiley and Sons. New York. 1961
421
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66. Hsu, Pa Ho and D. A. Rennie, Reactions of phosphate in aluminum
systems: I. Adsorption of phosphate by X-ray amorphous aluminum
hydroxide. Can. J. Soil Sci. 43: 197-209. 1962
67. Rennie, D. A, and R. B. McKercher. Adsorption of phosphorus by
four Saskatchewan soils. Can. J. Soil Sci. 39: 64-75. 1959
68. Weir, C. C. and R. J. Soper. Adsorption and exchange studies of
phosphorus in some Manitoba soils. Can. J. Soil Sci. 42: 31-42.
1962
69. Seatz, L. F. Phosphate activity measurements in soils. Soil Sci.
77: 43-51. 1954
70, Dalton, J. D., G. C. Russel and D. H. Sieling. Effect of organic
matter on phosphate availability. Soil Sci. 73: 173-181. 1952
71. Doughty, J. L, Phosphate fixation in soils, particularly as
influenced by organic matter. Soil Sci. 40: 191-202. 1935
72. Swenson, R, M., C. V. Cole and D. H. Sieling. Fixation of phos-
phate by iron and aluminum and replacement by organic and inorganic
ions. Soil Sci. 67: 3-22. 1949
73. Jackson, M, L. Soil Chemical Analysis. Prentice-Hall. Englewood
Cliffs, N. J. 1958
74. Bray, R. H. Correlation of soil tests with crop response to
added fertilizers and with fertilizer requirement. Diagnostic
Techniques. Chap. 11, pp 53-86. The American Potash Institute,
Washington, D. C. 1948
75. Eaton, F. M. and L. V. Wilcox. The behavior of boron in soils.
U.S.D.A. Tech. Bui. No. 696, pp 58. 1939
76. Olson, R. V. and K. C. Berger. Boron fixation as influenced by
pH, organic matter content and other factors. Soil Sci. Soc.
Am. Proc. 1946: 216-220. 1947
77. Parks, W. L. and J. L. White. Boron retention by clay and humus
systems saturated with various cations. Soil Sci. Soc. Am. Proc.
16: 298-300. 1952
78. Berger, K. C. and E. Truog. Boron determination in soils and
plants. Ind. Eng. Chem. Anal. Ed. 11: 540-545. 1939
79. Biggar, J. W. and M. Fireman. Boron adsorption and release by
soils. Soil Sci. Soc. Am. Proc. 24: 115-120. 1960
80. Sims, J. R. and F. T. Bingham. Retention of boron by layer sili-
cates, sesquioxides and soil materials: II Sesquioxides. Soil
Sci. Soc. Am. Proc. 32: 364-369. 1968
422
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81. Baker, D. E., et al. Techniques of rapid analysis of corn leaves
for eleven elements, Agron. J. 56: 133-136. 1964
82. Hatcher, J. T, and L. V. Wilcox. Colorimetric determination of
boron using carmine. Anal, Chem. 22: 567-569. 1950
83. Stolzy, L. H. and J. Letey. Correlation of plant response to
soil oxygen diffusion rates. III. Hilgardia, Vol. 35, No. 20,
Oct., 1964
84. Van Diest, A. Effect of soil aeration and compaction on yield,
nutrient uptake, and variability in a greenhouse fertility experi-
ment. Agron. J. 54: 515-518. 1962
85. ^Cannon, W. A. Physiological features of roots with special
reference to the relation of roots to the aeration of the soil.
Carnegie Inst. Washington Pub. No. 368. 1925
86. Wiegand, C. L. and E. R. Lemon. A field study of some plant-soil
relations in aeration. Soil Sci. Soc. Am. Proc. 22: 216-221.
1958
87, Allison, F. E., J.. N. Carter and L. D. Sterling. The effect of
partial pressure of oxygen on denitrification in soil. Soil Sci.
Soc. Am. Proc. 24: 283-285. 1960
88. Jones, S. J. Loss of elemental nitrogen from soils under anaero-
bic conditions. Soil Sci. 71: 193-196. 1951
89. Miller, R. D. and D. D. Johnson. The effect of soil moisture
tension on carbon dioxide, nitrification, and nitrogen minerali-
zation. Soil Sci. Soc. Am. Proc, 28: 644-647. 1964
90. Patrick, W. H. and R. Hyatt. Soil nitrogen loss as a result of
alternate submergence and drying. Soil Sci. Soc. Am. Proc. 28:
647-653. 1964
91. Piper, C. S. The availability of manganese in the soil. J. Agr.
Sci. 21: 762-779. 1931
92. Godden, W. and R. E. Grimraett. Factors affecting the iron and
manganese content of plants with special reference to herbage
causing "pinning" and "brush sickness". J. Agr. Sci. 18: 363-
368. 1928
93. Islam, M. A. and M. A. Elahi. Reversion of ferric iron to ferrous
iron under waterlogged conditions and its relation to available
phosphorus. J. Agr. Sci. 45: 1-2. 1954
423
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94. Peech, M., et al. Methods of soil analysis for soil fertility
investigations. U.S.D.A. Circ. No. 757. 25 pp. 1947
95. Kimball, B. F. Assignment of frequencies to a completely ordered
set of sample data. EOS. Trans. AGU 27: 843. 1946
96. Parizek, R. R. Permeability development in folded and faulted
carbonates. EOS.. Trans. AGU 50: 155. 1969
97. Siddiqui, S. H. and R, R. Parizek. Hydrogeologic factors in-
fluencing well yields in folded and faulted carbonate rocks of
Central Pennsylvania. Water Resources Res. 7: 1295-1312. 1971
98. Parizek, R. R. Hydrogeologic framework of folded and faulted
carbonates-influence of structure. Mineral Conservation Circular
Series No. 82. pp. 28-34. The Pennsylvania State Univ. 1972
99. Thornthwaite, C. W. and J. R. Mather. The water balance. Clima-
tology 8: 1-104, Drexel Institute of Technology Laboratory of
Climatology, Centerton, N. J. 1955
100. Thornthwaite, C. W. and J. R. Mather, Instruction and tables for
computing potential evapotranspiration and the water balance.
Climatology 10: 184-311. Drexel Inst. of Tech. Lab. of Clima-
tology, Centerton, N. J. 1957
101. Siddiqui, S. H. Hydrogeologic factors influencing well yields
and aquifer hydraulic properties of folded and faulted carbonate
rocks in central Pennsylvania. Ph.D. Thesis. Dept. of Geo-
sciences. The Pennsylvania State University. 1969
102. Parizek, R. R. Waste Water Renovation and Conservation Project.
pp 153-170 in Hydrogeology and Geochemistry of Folded and Faulted
Rocks of the Central Appalachian Type and Related Land Use
Problems by R. R. Parizek, W. B. White and D. Langmuir. Guide-
book, Geol. Soc. of Am. Washington, D. C. 1970
103. Kbnikow, L. F. MDuntain runoff and its relationship to recharge
to the carbonate aquifer of Nittany valley, Pennsylvania.
pp 79-85 in source cited in reference No. 102. 1970
104. Smith, R. E. Petrographic properties influencing porosity and
permeability in the carbonate-quartz system represented by the
Gatesburg formation. Ph.D. Thesis, Dept. of Geosciences, The
Pennsylvania State Univ. 1966
105. Parizek, R. R. and E. A. Myers. Recharge of ground water from
renovated sewage effluent by spray irrigation. Proc. 4th Am.
Water Resources Conf. pp 426-443. 1967
424
-------
106, Theis, C, V, The spacing of pumped wells. U.S. Geol. Surv.,
Ground Water Branch, Ground Water Notes, Hydraulics No. 31.
Open Fiel Rpt, 1957
107, Wenzel, L. K. and V. C. Fishel. Methods for determining perme-
ability of water bearing material. U.S. Geol. Survey Water
Supply Paper 887: 192. 1942
108, Parizek, R. R. and S. H. Siddiqui. Determining the sustained
yields of wells in carbonate and fractured aquifers. Ground
Water 8(5): 12-20. 1969
109. Ackerman, W. C. Cost of pumping water. Ground Water 7(1): 38-
39. 1969
110, Allender, G. C. The cost of a spray irrigation system for the
renovation of treated municipal wastewater. M.S. Thesis, Dept.
of Civil Engineering, The Pennsylvania State University. 1972
111. Allender, G. C. Personal poll of seven industries using spray
irrigation (unpublished). Dept. of Civil Eng., The Pennsylvania
State Univ. 1967
112. Muskegon County Board and Dept. of Public Works. Engineering
feasibility demonstration study for Muskegon County, Mich, waste-
water treatment-irrigation system. Water Poll. Contr. Res. Ser.
11010 EMT 10/70. 174 pp. Sept. 1970. U.S. Dept. Int., Fed. Water
Quality Adm.
425
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SECTION XII
PUBLICATIONS
Theses and Publications Derived from the Penn State Waste Water
Renovation and Conservation Research. 1963-1969.
1, Carrucio, F. T. The hydrogeology of the sewage disposal experi-
ment area northwest of State College, Pennsylvania. M. S. Thesis,
Dept. of Geology and Geophysics, The Pennsylvania State University,
2. Landon, R. A. The geology of the Gatesburg formation in the
Belief onte Quadrangle, Pennsylvania, and its relationship to
general occurrence and movement of groundwater. M. S. Thesis,
Dept. of Geology and Geophysics, The Pennsylvania State University,
1963.
3. Clark, J. H. Geology of the Ordovician carbonate formations in the
State College, Pennsylvania area, and their relationships to the
general occurrence and movement of groundwater. M. S. Thesis, Dept.
of Geology and Geophysics, The Pennsylvania State University, 1965.
4. Parmele, L. H. A comparison and evaluation of methods for distrib-
uting waste water in wooded areas. M. S. Thesis, Dept. of
Agricultural Engineering, The Pennsylvania State University, 1964.
5. Givens, F. G., Jr. The development of irrigation sprinkler heads
for winter distribution of treated sewage effluent in wooded areas.
M. S. Thesis, Dept. of Agricultural Engineering, The Pennsylvania
State University, 1965.
6. Pennypacker, S. P. Renovation of sewage effluent through irriga-
tion of forest land. M. S. Thesis, Dept. of Forest Management,
The Pennsylvania State University, 1964.
7. Sagmuller, C. J. Mixed oak, red pine, and old field plant responses
to irrigation with municipal sewage effluent. M. S. Thesis, Dept.
of Forest Management, The Pennsylvania State University, 1965.
8. Kline, G. N. Effect of sewage effluent on the chemical properties
of the soil in a hardwood stand, red pine plantation, and open old
field, M. S. Thesis, Dept. of Forestry and Wildlife, The Pennsyl-
vania State University, 1967.
9. Myers, J. C. A study of drainage conditions on a hillside receiving
sewage plant waste water effluent at weekly intervals. M. S. Thesis,
Dept. of Agronomy, The Pennsylvania State University, 1968.
427
-------
10. Edwards, I. K. The renovation of sewage plant effluent by the
soil and by agronomic crops. Ph. D, Thesis, Dept, of Agronomy,
The Pennsylvania State tftiiversity, 1968.
11. Rebuck, E. C. The hydrologic regijne due to sprinkler irrigation
of treated Municipal effluent on sloping land. M. S. Thesis,
Dept. of Agricultural Engineering, The Pennsylvania State univer-
sity, 1967.
12. Brown, C. D. The development of stationary-orifice rotation
deflector sprinkler heads for distribution of treated sewage
effluent. M. S. Thesis, Dept. of Agricultural Engineering, The
Pennsylvania State University, 1967.
13, Kardos, L. T., W. E. Sopper and E. A. Myers. Sewage effluent
renovated through application to farm and forest land. Sci. for
the Farmer 12(4):4, 1965.
14. Pennypacker, S. P., W. E. Sopper and L. T. Kardos, Renovation of
waste water effluent by irrigation of forest land. Jour. Water
Poll. Contr. Fed. 39(2) 285-296, 1967.
15. Sopper, W. E. Renovation of municipal sewage effluent for ground-
water recharge through forest irrigation. International Conf. on
Water for Peace. Proc. Vol. 2: pp 534-544, Washington, D. C. 1967.
16. Kardos, L. T. Waste water renovation by the land - A living
filter, pp. 241-250. AAAS Pub. No. 85. Agriculture and the
Quality of Our Environment. N. C. Brady, Editor. 1967.
17. Myers, E. A. Engineering problems in year-round distribution of
waste water. Proc. Natl. Syrap. on Animal Waste Management. Am.
Soc. Agr. Eng. Pub. No. SP-0366, St. Joseph, Michigan. 1966.
18. Parizek, R. R., L. T. Kardos, W. E. Sopper, E. A. Myers, D. E.
Davis, M. A. Farrell and J. B. Nesbitt. Waste Water Renovation
and Conservation. Penn State Studies No. 23. 7; pp. 1967.
19. Glantz, P. J. and T. M. Jacks. Significance of Escherichia Coli
serotypes in wastewater effluent. Jour. Water Poll. Contr. Fed.
39: 1918-1921, 1967.
20. Sagmuller, C. J. and W. E. Sopper. Effect of municipal sewage
effluent irrigation on height growth of white spruce. Jour, of
Forestry 66: 822-823, 1967.
21. Sopper, W. E. Effects of sewage effluent irrigation on tree
growth. Pennsylvania Forests 58: 23-26, 1968.
428
-------
22. Sopper, W. E. Waste water renovation for re-use. Key to optimum
use of water resources. Water Research 2: 471-480, 1968.
23. Kardos, L. T., W. E. Sopper and E. A. Myers. A living filter for
sewage. Yearbook of Agriculture - Science for Better Living.
pp. 197-201, 1968.
24. Kardos, L. T., Waste disposal on the land - the living filter
concept. Proc. 15th National Watershed Conference. May 26-29,
1968. pp. 75-81.
25. Kardos, L. T., Crop response to sewage effluent. Proc. Symposium
on Sewage Effluent for Irrigation La. Poly. Inst. July 30, 1968.
pp. 21-29.
26. Klausner, S. D., Oxygen relationships on a soil treated with
sewage effluent. M.S. Thesis, Dept. of Agronomy, The Pennsylvania
State University, 1968, 99 pp.
27. Kardos, L. T. The living landscape filter. Landscape Architure
59(3): 205-206, 1969.
28. Sopper, W. E. and C. J. Sagmuller. Forest vegetation growth
responses to irrigation with municipal sewage effluent. Proc.
Pan American Soil Conservation Congress, Sao Paulo, Brazil, 1966.
pp. 639-647.
29. Myers, Earl A. Sprinkler irrigation disposal of liquid wastes.
Proc. Food Industry Waste Management Conference. The Pennsylvania
State Univ. pp. 70-74, May, 1969.
30. Myers, E. A. and G. R. Bodman. Sprinkler distribution of waste-
water under freezing conditions. Proc. 7th Int. Congress of Agric.
Eng. Baden Baden, Germany, pp. 218-224. October, 1969.
31. Kardos, L. T. Research in pollution control, pp. 141-145 in
Research for the World Food Crisis. A.A.A.S. Symposium, Dec.
1968, Dallas, Tex. Pub. No. 92, A.A.A.S., Washignton, D. C. 1970.
32. Kardos, L. T. Waste water renovation by the land. The Izaak
Walton Magazine, Outdoor America: page 3, June, 1967.
429
-------
SECTION XIII
APPENDICES
Page No.
A. Tables
A-l Average Nutrient Composition (Percent) of Crop
Receiving Various Levels of Sewage Effluent Per
Week - 1963 436
A-2 Average Nutrient Composition (in Percent or Micro-
grams Per Gram) of Crop Receiving Various Levels
of Sewage Effluent Per Week - 1964 437
A-3 Average Nutrient Composition (Percent) of Crop
Receiving Various Levels of Sewage Effluent Per
Week - 1963 438
A-4 Average Nutrient Composition (in Percent or Micro-
grams Per Gram) of Crops Receiving Various Levels
of Sewage Effluent Per Week - 1965 439
A-5 Average Nutrient Composition (in Percent or Micro-
grams Per Gram) of Crops Receiving Various Levels
of Sewage Effluent Per Week - 1966 440
A-6 Average Nutrient Composition (in Percent or Micro-
grams Per Gram) of Crop Receiving Various Levels
of Sewage Effluent Per Week - 1967 441
A-7 Average Nutrient Composition (in Percent or Micro-
grams Per Gram) of Reed Canarygrass Receiving Two
Inches of Sewage Effluent Per Week - 1965 442
A-8 Average Nutrient Composition (in Percent or Micro-
grams Per Gram) of Reed Canarygrass Receiving Two
Inches of Sewage Effluent Per Week - 1966 443
A-9 Average Nutrient Composition (in Percent or Micro-
grams Per Gram) of Reed Canarygrass Receiving Two
Inches of Sewage Effluent Per Week - 1967 444
A-10 Average Nutrient Composition (in Percent or Micro-
grams Per Gram) of Reed Canarygrass Receiving Two
Inches of Sewage Effluent Per Week - 1968 445
A-11 Average Nutrient Composition (in Percent or Micro-
grams Per Gram) of Reed Canarygrass Receiving Two
Inches of Sewage Effluent Per Week - 1969 445
431
-------
Page No.
A. Tables (Continued)
A-12 Quantities of Nutrients (Pounds Per Acre) Removed
by Crops Receiving Various Levels of Sewage
Effluent Per Week - 1963 447
A-13 Quantities of Nutrients (Pounds Per Acre) Removed
by Crops Receiving Various Levels of Sewage
Effluent Per Week - 1964 448
A-14 Quantities of Nutrients (Pounds Per Acre) Removed
by Crops Receiving Various Levels of Sewage
Effluent Per Week - 1963 449
A-15 Quantities of Nutrients (Pounds Per Acre) Removed
by Crops Receiving Various Levels of Sewage
Effluent Per Week - 1965 450
A-16 Quantities of Nutrients (Pounds Per Acre) Removed
by Crops Receiving Various Levels of Sewage
Effluent Eer Week - 1966 451
A-17 Quantities of Nutrients (Pounds Per Acre) Removed
by Crops Receiving Various Levels of Sewage
Effluent Per Week - 1967 452
A-18 Quantities of Nutrients (Pounds Per Acre) Removed
by Reed Canarygrass Receiving Two Inches of Sewage
Effluent Per Week - 1965 453
A-19 Quantities of Nutrients (Pounds Per Acre) Removed
by Reed Canarygrass Receiving Two Inches of Sewage
Effluent Per Week - 1966 454
A-20 Quantities of Nutrients (Pounds Per Acre) Removed
by Reed Canarygrass Receiving Two Inches of Sewage
Effluent Per Week - 1967 455
A-21 Quantities of Nutrients (Pounds Per Acre) Removed
by Reed Canarygrass Receiving Two Inches of Sewage
Effluent Per Week - 1968 456
A-22 Quantities of Nutrients (Pounds Per Acre) Removed
by Reed Canarygrass Receiving Two Inches of Sewage
Effluent Per Week - 1969 457
432
-------
Page No.
A. Tables (Continued)
A-23 Chemical Composition of the Sewage Effluent and
Amounts of Constituents Applied on the 2-inches Per
Week Plots During 1965 453
A-24 Average Concentration of Constituents in the
Combined Effluent and Storm Percolate Samples from
Tension Lysimeters of the Original Forestry Plots
(Farm Woodlot Site) During the Irrigation Period
4/20/65 to 11/16/65 459
A-25 Average Concentration of Constituents in the
Percolate Samples of the Original Forestry Control
Plots (Farm Woodlot Site) During the Period
4/20/65 to 11/16/65 460
A-26 Chemical Composition of Sewage Effluent Applied on
Original Forestry Experimental Plots (Farm Woodlot
Site) During the Period 4/5/66 to 11/16/66 461
A-27 Average Concentration of Constituents in the
Combined Effluent and Storm Percolate Samples of
the Original Forestry Plots (Farm Woodlot Site)
During the Irrigation Period 4/5/66 to 11/15/66 462
A-28 Average Concentration of Constituents in the
Percolate Samples of the Original Forestry Control
Plots (Farm Woodlot Site) During the Period
4/2/66 to 11/15/66 463
A-29 Chemical Composition of Sewage Effluent Applied on
Original Forestry Experimental Plots (Farm Woodlot
Site) During the Period 4/18/67 to 10/31/67 454
A-30 Average Concentration of Constituents in the
Combined Effluent and Storm Percolate Samples of
the Original Forestry Plots (Farm Woodlot Site)
During the Irrigation Period 4/18/67 to 10/31/67 465
A-31 Average Concentration of Constituents in the
Percolate Samples of the Original Forestry Control
Plots (Farm Woodlot Site) During the Period
4/18/67 to 10/31/67 466
A-32 Chemical Composition of Sewage Effluent Applied on
Original Forestry Experimental Plots (Farm Woodlot
Site) During the Period 4/9/68 to 11/12/68 467
433
-------
Page
A. Tables (Continued)
A-33 Average Concentration in Percolate Samples and in
the Sewage Effluent for the Original Forestry Plots
(Farm Woodlot Site) During the Irrigation Period
4/9/68 to 11/12/68 468
A-34 Average Concentration of Constituents in the
Percolate Samples of the Original Forestry Control
Plots (Farm Woodlot Site) During the Period
4/9/68 to 11/12/68 470
A-35 Average Concentration of Percolate Samples and of
Sewage Effluent in the New Red Pine - 2 inches Per
Week Area. 1965 and 1966 471
A-36 Average Concentration in Percolate Samples and in
Sewage Effluent for the New Red Pine - 2 inches Per
Week Area. 1967 and 1968 472
A-37 Average Concentration of Percolate Samples and of
Sewage Effluent in the New Gamelands Area. 1966
and 1967 473
A-38 Average Concentration of Percolate in the Hardwood
Control Plot at the New Gamelands Site. 1966 and
1967 474
A-39 Average Concentration in Percolate Samples and
Sewage Effluent for the Hardwoods New Gamelands
Area which Received 2 Inches of Effluent Per Week
During the Period 1/1/68 to-12/31/68 and for a
Nearby Control Area 475
A-40 Average Concentration of Constituents in the
Percolate at Various Soil Depths on the Plot
which Received 4 Inches Per Week During 1965 476
A-41 Average Concentration of Constituents in the
Percolate Samples Collected from Pan Lysimeters
Located in the Hardwood Plot which Received 4
Inches of Effluent Per Week During the Period
4/5/66 to 11/17/66 477
A-42 Average Concentration of Constituents in the
Percolate Samples Collected from Pan Lysimeters
Located in the Hardwood Plot which Received 4
Inches of Effluent Per Week During the Period
4/18/67 to 10/31/67 478
434
-------
Page No.
A. Tables (Continued)
A-43 Mean Nutrient Element Concentration of the Soil
Samples Collected in 1963, 1964, and 1965 in the
Red Pine 1-inch Treatment and Control Plots 479
A-44 Mean Chemical Element Concentration of the Soil
Samples Collected in 1963, 1964, and 1965 in the
Red Pine 2-inch Treatment and Control Plots 481
A-45 Mean Nutrient Element Concentration of the Soil
Samples Collected in 1963, 1964, 1965 in the Open
Area 2-inch Treatment and Control Plots 483
435
-------
Table A-l. Average Nutrient Composition (Percent) of Crop Receiving Various Levels of Sewage
Effluent Per Week - 1963
O\
Crop and Inches of Effluent Applied Per Week
RED CLOVER
Nutrient
Nitrogen
Phosphorus
Potassiun
Calciun
Magnesium
0
1.74
0.185
1.99
0.913
0.134
1st Cut
1
2.28
0.262
2.73
1.428
0.217
2
2.46
0.234
2.69
1.402
0.214
0
2.09
0.276
2.25
1.334
0.214
2nd Cut
1
2.13
0.271
2.65
1.135
0.240
Weighted Averages
2
2.15
0.293
2.62
1.208
0.255
0
1.86
0.217
2.08
1.060
0.162
1
2.21
0.266
2.69
1.296
0.227
2
2.29
0.266
2.65
0.298
0.236
-------
01
Table A-2. Average Nutrient Composition (in Percent or Micrograms Per Gram) of Crop Receiving
Various Levels of Sewage Effluent Per Week - 1964
Crop and Inches of Effluent Applied Per Week
RED CLOVER
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
0
1.97
0.187
1.90
0.621
0.129
0.41
1st Cut
1
2.44
0.300
3.05
0.900
0.295
1.06
1.
0.
2.
0.
0.
1.
2
93
264
69
606
211
28
0
2.35
0.214
1.89
0.938
0.197
0.36
2nd Cut
1
Percent
3.22
0.371
3.09
1.034
0.350
1.07
Micrograms Per
Weighted Averages
3.
0.
2.
0.
0.
1.
2
13
345
98
715
270
21
0
2.03
0.191
1.90
0.672
0.140
0.40
1
2.72
0.326
3.06
0.948
0.315
1.06
2
2.38
0.294
2.79
0.653
0.233
1.25
tSrams
Boron
14
24
13
22 29 18
15
26
15
-------
Table A-3. Average Nutrient Composition (Percent) of Crop Receiving Various Levels of Sewage
Effluent Per Week - 1963
-is.
W
CO
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
0
1.40
0.224
1.91
0.530
0.109
1st Cut
1
1.89
0.244
2.12
0.823
0.145
Crop and
2
1.72
0.271
2.09
0.463
0.121
Inches of Effluent Applied Per Week
ALFALFA
0
2.49
0.292
2.04
0.891
0.150
2nd Cut
1
1.95
0.375
2.39
0.513
0.160
Weighted Averages
2
2.05
0.362
2.51
0.417
0.165
0
1.75
0.245
1.95
0.646
0.122
1
1.92
0.308
2.25
0.670
0.152
2
1.87
0.313
2.28
0.442
0.141
-------
Table A-4. Average Nutrient Composition (in Percent or Micrograms Per Gram) of Crops Receiving
Various Levels of Sewage Effluent Per Week - 1965.
Nutrient
Crop and Inches of Effluent .Applied Per Week
ALFALFA
1st Cut 2nd Cut 3rd Cut
0
0
Weighted Averages
_ _ _
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
1.68 2.30 2.06
0.174 0.248 0.279
2.00 2.39 2.72
0.849 0.647 0.665
0.116 0.215 0.241
0.47 0.95 1.12
Percent
3.20 3.36 3.33
0.201 0.324 0.317
1.40 2.36 2.43
0.919 0.642 0.689
0.140 0.211 0.199
0.37 1.17 1.14
3.26 2.98 3.21
0.217 0.391 0.386
2.18 3.11 3.22
1.353 0.649 0.612
0.176 0.224 0.215
0.71 1.68 1.63
2.12 2.66 2.62
0.185 0.293 0.312
2.04 2.55 2.75
0.980 0.647 0.660
0.132 0.216 0.225
0.53 . 1.16 1.23
Boron
14
18
22
Micrograms Per Gram
11 13 16 17
17
14
16
19
-------
Table A-5. Average Nutrient Composition (in Percent or Micrograms Per Gram) of Crops Receiving
Variolas Levels of Sewage Effluent Per Week - 1966
•p.
o
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Crop and Inches of Effluent Applied Per Week
ALFALFA
1st Cut 2nd Cut 3rd Cut
Weighted Averages
012
Percent
1.90 1.42 1.25
0.246 0.311 0.340
1.05 1.07 1.16
0.42 0.31 0.28
0.18 0.20 0.20
0.33 0.40 0.39
2.30 1.99 1.92
0.260 0.337 0.282
2.36 2.59 2.50
0.79 0.68 0.52
0.18 0.22 0.20
0.83 1.22 1.33
3.67 2.89 2.58
0.293 0.380 0.377
1.81 2.38 2.59
0.66
1.06
0.14 0.22
0.63 1.31
Sodium
Boron
13
5
250
5
211
5
25
12
327
14
248
11
24 i
18
Micrograms Per Gram
272
12
0.56
0.21
1.39
272
10
2.91 2.35 2.14
0.244 0.327 0.330
2.48 2.83 2.78
1.03 0.66 0.54
0.15 0.20 0.19
0.55 1.07 1.22
23
17
224
14
197
10
-------
Table A-6. Average Nutrient Composition (in Percent or Micrograms Per Gram) of Crop Receiving
Various Levels of Sewage Effluent Per Week - 1967
Crop and Inches of Effluent Applied Per Week
ALFALFA
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
0
1.32
0.21
2.05
0.54
0.11
0.62
1st Cut
1
1.28
0.24
2.29
0.39
0.13
0.91
2
1.46
0.25
2.42
0.36
0.14
1.12
0
2.46
0.32
2.42
1.46
0.20
0.61
2nd Cut
1
Percent
2.36
0.42
2.72
0.55
0.19
1.48
Micrograms Per
Sodium
Boron
26
10
154
8
121
7
38
26
155
12
Weighted Averages
2
3.52
0.40
2.76
0.46
0.19
1.33
Gram
235
10
0
1.82
0.26
2.21
0.95
0.15
0.62
31
17
1
1.54
0.28
2.39
0.43
0.14
1.04
154
9
2
2.10
0.30
2.53
0.39
0.16
1.18
157
8
-------
Table A-7. Average Nutrient Composition (in Percent or Micrograms
Per Gram) of Reed Canarygrass Receiving Two Inches of
Sewage Effluent Per Week - 1965
Nutrient
Nitrogen
Phosphorus
Potassiun
Calcium
Magnesium
Chloride
Sodium
Boron
1st Cut
2.44
0.32
2.58
0.44
0.24
1.38
482
9
2nd Cut
Percent
3.29
0.27
2.35
0.64
0.22
1.52
Micrograms Per Gram
267
8
3rd Cut
3.46
0.47
3.11
0.51
0.33
1.95
488
8
Weighted
Averages
3.00
0.33
2.63
0.54
0.25
1.56
408
8
442
-------
Table A-8. Average Nutrient Composition (in Percent or Micrograms
Per Gram) of Reed Canarygrass Receiving Two Inches of
Sewage Effluent Per Week - 1966
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Sodium
Boron
1st Cut
3.18
0.36
3.06
0.34
0.20
1.39
117
7
2nd Cut
Percent
3.18
0.44
2.90
0.31
0.26
1.54
Micrograms Per Gram
151
3
3rd Cut
2.85
0.40
1.80
0.37
0.20
1.11
224
6
Weighted
Averages
3.15
0.39
2.90
0.33
0.22
1.41
137
6
443
-------
Table A-9. Average Nutrient Composition (in Percent or Micrograms
Per Gram) of Reed Canarygrass Receiving Two Inches of
Sewage Effluent Per Week - 1967
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Sodium
Boron
1st Cut
2.21
0.36
2.58
0.44
0.27
1.34
332
7
2nd Cut
Percent
2.59
0.42
2.62
0.41
0.28
1.60
Micrograms Per Gram
259
8
3rd Cut
2.35
0.47
1.80
0.58
0.35
1.50
441
6
Weighted
Averages
2.34
0.40
2.44
0.46
0.29
1.44
334
7
444
-------
Table A-10. Average Nutrient Composition (in Percent or Micrograms
Per Gram) of Reed Canarygrass Receiving Two Inches of
Sewage Effluent Per Week - 1968
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Sodium
Boron
1st Cut
Percent
4.09
0.46
3.00
0.47
0.27
0.27
Micrograms Per
360
5
2nd Cut
2.65
0.47
1.79
0.30
0.28
0.28
Gram
224
5
Weighted
Averages
3.50
0.46
2.50
0.40
0.28
0.28
304
5
445
-------
Table A-ll. Average Nutrient Composition (in Percent or Micrograms
Per Gram) of Reed Canarygrass Receiving Two Inches of
Sewage Effluent Per Week - 1969
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Sodium
Boron
1st Cut
3.54
0.39
2.23
0.47
0.39
2.09
325
11
2nd Cut
Percent
3.36
0.52
1.86
0.46
0.29
1.14
Micrograms Per Gram
124
9
3rd Cut
3.06
0.57
1.92
0.50
0.33
1.27
328
12
Weighted
Averages
3.42
0.45
2.07
0.47
0.35
1.67
259
11
446
-------
Table A-12. Quantities of Nutrients (Pounds Per Acre) Removed by Crops Receiving Various Levels
of Sewage Effluent Per Week - 1963
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
0
56.0
6.0
64.2
29.4
4.3
1st Cut
1
123.1
14.1
147.3
77.1
11.7
Crop and
2
105.3
10.0
115.0
60.0
9.2
Inches of Effluent Applied Per Week
RED CLOVER
0
36.4
4.8
39.2
23.2
3.7
2nd Cut
1
93.7
11.9
116.8
49.9
10.6
Total Quantities
2
105.4
14.4
128.5
59.2
12.5
0
91.4
10.8
103.4
52.6
8.0
1
216.8
26.0
264.1
127.0
22.3
2
210.7
24.4
243.5
119.2
21.7
-------
Table A-13. Quantities of Nutrients (Pounds Per Acre) Removed by Crops Receiving Various Levels
of Sewage Effluent Per Week - 1964
oo
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Boron
0
58.3
5.6
56.2
18.4
3.8
12.1
0.04
1st Cut
1
164.9
20.3
206.2
60.8
20.3
71.6
0.17
Crop and
2
124.3
16.7
173.2
39.3
13.5
82.4
0.08
Inches of Effluent Applied Per Week
RED CLOVER
0
13.2
1.2
10.6
5.3
1.1
2.0
0,01
2nd Cut
1
123.6
14.2
118.6
39.6
13.4
41.1
0.11
Total Quantities
2
118.9
12.9
113.2
27.4
10.3
46.0
0.07
0
71.5
6.8
66.8
23.7
4.9
14.1
0.05
1
288.5
34.5
324.8
100.4
33.7
112.7
0.28
2
243.2
29.6
286.4
66.7
23.8
128.4
0.15
-------
Table A-14. Quantities of Nutrients (Pounds Per Acre) Removed by Crops Receiving Various Levels
of Sewage Effluent Per Week - 1963
Crop and Inches of Effluent Applied Per Week
ALFALFA
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
0
41.4
6.6
56.4
15.7
3.2
1st Cut
1
71.4
9.2
79.9
31.1
5.5
2
94.9
15.0
115.5
25.6
6.7
0
34.9
4.1
28.6
12.5
2.1
2nd Cut
1
71.8
13.8
88.0
18.9
5.9
Total Quantities
2
96.8
17.0
118.5
19.7
7.8
0
76.1
10.7
85.0
28.2
5.3
1
143.2
23.0
167.9
50.0
11.4
2.
191.7
32.0
234.0
45.3
14.5
-------
Table A-15. Quantities of Nutrients (Pounds Per Acre) Removed by Crops Receiving Various -Levels
of Sewage Effluent Per Week - 1965
en
o
Crop and Inches of Effluent Applied Per Week
ALFALFA
1st Cut
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Boron
0
54.8
5.7
65.2
27.7
3.8
15.3
0.04
1
125.1
13.5
130.0
35.2
11.7
51.7
0.10
2
120.7
16.3
159.4
39.0
14.1
65.6
0.13
0
3.2
0.2
1.4
0.9
0.1
0.4
0.01
2nd Cut
1
59.8
5.8
42.0
11.4
3.8
20.8
0.02
2
91.9
8.7
67.1
19.0
5.5
31.5
0.04
3rd Cut
0
38.5
2.6
25.7
16.0
2.1
8.4
0.02
1
63.2
8.3
65.9
13.8
4.7
35.6
0.04
2
71.3
8.6
71.5
13.6
4.8
36.2
0.04
Total
0
96.5
8.5
92.3
44.6
6.0
24.1
0.07
Quantities
1 2
248.1 283.9
27.6 33.6
237.9 298.0
60.5 71.6
20.2 24.4
108.1 133.3
0.16 0.21
-------
cn
I-1
Table A-16. Quantities of Nutrients (Pounds Per Acre) Removed by Crops Receiving Various Levels
of Sewage Effluent Per Week - 1966
Crop and Inches of Effluent Applied Per Week
ALFALFA
1st Cut
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Sodium
Boron
0
86.7
7.0
74.6
30.0
4.2
86.7
0.07
0.03
1
103.3
13.4
133.0
28.5
7.7
103.3
0.67
0.06
2
90.1
14.7
127.5
22.8
7.1
90.1
0.71
0.04
2nd Cut
0
14.5
1.8
16.0
5.0
1,1
14.5
0.04
0.01
1
43.5
7.4
59.3
16.1
4.9
43.5
0.83
0.03
2
57.5
8.4
76.5
15.8
6.1
57.5
0.76
0.03
3rd Cut
0
11.2
0.9
5.2
2.7
0.4
11.2
0.01
0.01
1
32.8
4.2
27.2
7.3
2.5
32.8
0.31
T 0.01
2
37.2
5.5
38.1
8.0
3.0
37.2
0..39
0.01
Total
0
112.4
9.7
95.8
37.7
5.7
21.4
0.12
0.07
Quantities
1 2
179.6 184.8
25.0 28.6
219.5 242.1
51.9 46.6
15.1 16.2
83.0 105.5
1.81 1.86
0.10 0.08
-------
Table A-17. Quantities of Nutrients (Pounds Per Acre) Removed by Crops Receiving Various Levels
of Sewage Effluent Per Week - 1967
en
NJ
Crop and
Nutrient
Nitrogen
Phosphorus
Pot ass run
Calcium
Magnesium
Chloride
Sodium
Boron
0
37.9
5.6
52.8
12.9
2.7
14.8
0.06
0.02
1st Cut
1
72.9
13.8
132.5
22.2
7.6
51.1
0.88
0.05
2
75.
14.
143.
21.
8.
65.
0.
0.
6
9
2
6
0
2
72
04
Inches of Effluent
ALFALFA
0
32.1
3.0
21.8
12.9
1.9
5.6
0.03
0.02
2nd Cut
1
42.0
7.5
48.6
9.6
3.4
26.4
0.28
0.02
Applied Per Week
Total Quantities
2
57.3
9.4
65.8
10.4
4.3
29.6
0.55
0.04
0
70
8
74
25
4
20
0
0
.0
.6
.6
.8
.6
.4
.09
.04
1
114.9
21.3
181.1
31.8
11.0
77.5
1.16
0.07
2
132.9
24.3
209.0
32.0
12.4
94.8
1.27
0.08
-------
Table A-18. Quantities of Nutrients (Pounds Per Acre) Removed by
Reed Canary-grass Receiving Two Inches of Sewage Effluent
Per Week - 1965
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Sodium
Boron
1st Cut
131.8
17.9
142.7
23.7
13.2
77.2
2.54
0.05
2nd Cut
155.2
13.1
119.4
28.4
10.3
73.0
1.30
0.03
3rd Cut
66.1
9.0
59.8
9.9
6.3
37.4
0.92
0.02
Total
353.1
40.0
321.9
62.0
29.8
187.6
4.76
0.10
453
-------
Table A-19. Quantities of Nutrients (Pound Per Acre) Removed by
Reed Canarygrass Receiving Two Inches of Sewage Effluent
Per Week - 1966
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Sodium
Boron
1st Cut
163.4
18.4
157.3
17.5
10.3
71.4
0.60
0.03
2nd Cut
87.1
12.0
79.5
8.5
7.1
42.2
0.41
0.01
3rd Cut
21.7
3.0
13.7
2.8
1.5
8.4
0.17
0.01
Total
272.2
33.4
250.5
28.8
18.9
122.0
1.18
0.05
454
-------
Table A-20. Quantities of Nutrients (Pounds Per Acre) Removed by
Reed Canarygrass Receiving Two Inches of Sewage Effluent
Per Week - 1967
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Sodium
Boron
1st Cut
166.6
27.1
194.5
33.2
20.4
101.0
2.50
0.05
2nd Cut
97.4
15.8
98.5
15.4
10.5
60.2
0.97
0.03
3rd Cut
64.9
13.0
49.7
16.0
9.7
41.4
1.22
0.02
Total
328.9
55.9
342.7
64.6
40.6
202.6
4.69
0.10
455
-------
Table A-21. Quantities of Nutrients (Pounds Per Acre) Removed by
Reed Canarygrass Receiving Two Inches of Sewage Effluent
Per Week - 1968
Nutrient
1st Cut
2nd Cut
Total
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Sodium
Boron
254.4
27.6
180.0
28.2
16.2
118.2
2.16
0.03
110.8
19.6
74.8
12.5
11.7
51.4
0.93
0.02
356.2
47.2
254.8
40.7
27.9
169.6
3.09
0.05
456
-------
Table A-22. Quantities of Nutrients (Pounds Per Acre) Removed by
Reed Canarygrass Receiving Two Inches of Sewage Effluent
Per Week - 1969
Nutrient
Nitrogen
Phosphorus
Potassium
Calcium
Magnesium
Chloride
Sodium
Boron
1st Cut
200.4
22.1
126.2
26.6
22.1
118.3
1.84
0.06
2nd Cut
114.9
17.8
63.6
15.7
9.9
39.0
0.42
0.03
3rd Cut
39.2
7.3
24.6
6.4
4.2
16.2
0.42
0.02
Total
354.5
47.2
214.4
48.7
36.2
173.5
2.68
0.11
457
-------
Table A-23.
Chemical Composition of the Sewage Effluent and Amounts
of Constituents Applied on the 2-inches Per Week Plots
During 1965
Constituent
PH
MBAS
Nitrate -N
Organic-N±/
Phosphorus
Potassium
Calcium
Magnesium
Sodium
Chloride
Boron
Range
Min
mg/1
7.0
0.4
3.0
0.0
3.812
7.2
12.8
5.9
0.0
22.1
0.0
Max
mg/1
8.2
2.5
13.1
6.5
13.232
24.3
48.8
23.8
54.2
63.2
0.6,
Ave
mg/1
7.5
1.6
7.6
2.7
10.383
16.3
29.5
14.8
33.7
46.2
0.3
Total amount
applied
Ib/acre
22
103
36
122
199
360
181
459
545
4
I/
Includes ammoniacal nitrogen
458
-------
tn
Table A-24. Average Concentration of Constituents in the Combined Effluent and Storm Percolate
Samples from Tension Lysimeters of the Original Forestry Plots (Farm Woodlot Site)
During the Irrigation Period 4/20/65 to 11/16/65.
pH
ABS
N03-N
Org-N
P
K
Concentration in
Effluent Quality
Hardwood 1"
Forest Floor Pans
6" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
Red Pine 1"
Forest Floor Pans
6" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
Red Pine 2"
Forest Floor Pans
6" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
Old Field 2"
6" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
7.5
6.7
7.6
7.2
7.2
6.7
7.1
6.8
7.0
7.0
7.3
6.9
6.7
7.2
7.1
6.5
1.61
0.19
0.07
0.02
0.01
0.27
0.06
0.03
0.03
0.55
0.11
0.04
0.05
0.08
0.12
0.06
7.6
13.5
1.0
0.2
0.0
10.8
1.7
0.04
2.2
14.6
9.2
10.7
3.9
5.1
8.4
8.0
2.7
3.5
2.1
3.0
y
4.7
2/
175
1.3
3.1
2/
0.8
1.4
2/
077
0.8
10.383
5.061
.234
.390
.250
12.841
.178
.190
.300
6.858
0.335
.517
.400
.402
.116
.460
16.3
16.8
2/
9~. 8
6.3
16.4
2/
F.3
7.2
17.9
7.9
7.2
5.8
7.9
8.7
8.7
Ca
mg/1
29.5
22.0
2/
2T.1
12.2
30.6
2/
J.I
8.5
26.5
12.7
13.3
4.8
14.8
13.0
3.8
Mg
14.8
8.6
2/
IT.6
11.2
8.4
2/
3". 8
4.5
14.4
6.6
5.1
1.7
3.7
3.4
3.4
Na
33.7
20.7
2/
35". 2
8.3
23.3
2/
2ZF.9
8.5
32.1
39.2
40.1
22.5
33.4
33.4
29.1
Cl
46.2
28.0
49.5
84.7
20.3
36.5
58.0
49.1
14.3
43.9
98.3
91.2
38.9
45.5
44.5
44.8
2/ Insufficient sample volune for complete chemical analyses
-------
Table A-25.
Average Concentration of Constituents in the Percolate Samples of the Original
Forestry Control Plots (Farm Woodlot Site) During the Period 4/20/65 to 11/16/65
pH ABS
NO
3-N Ors-Nl/
P
Concentration
Hardwood 1"
6"
24"
48"
Red
6"
24"
48"
Red
6"
24"
48"
Old
6"
24"
48"
Tension
Tension
Tension
Pine 1"
Tension
Tension
Tension
Pine 2"
Tension
Tension
Tension
Field 2"
Tension
Tension
Tension
Control
Lysimeter
Lysimeter
Lysimeter
Control
Lysimeter
Lysimeter
Lysimeter
Control
Lysimeter
Lysimeter
Lysimeter
Control
Lysimeter
Lysimeter
Lysimeter
7.
8.
7.
7.
*
ft
7.
*
6.
6.
6.
6.
2 0.09
0 *
4 0.01
9 *
: ft
*
4 ft
! ft
9 *
9 0.02
8 0.02
8 0.05
0
30
0
0
0
0
0
0
.1 *
ft ft
.3 *
.3 *
* ft
ft ft
.1 *
ft ft
.9 *
.1 *
.0 0.5
.3 1.6
.065
.010
.050
ft
*
ft
.450
ft
.040
.065
.385
.395
K Ca
in ppm
ft ft
ft ft
W9 *»
ft ft
ft ft
ft ft
ft ft
ft ft
ft ft
ft ft
10.4 10.8
5.6 2.8
Mg
ft
*
A
ft
ft
*
ft
ft
ft
ft
3.3
1.0
Na
*
ft
ft
*
ft
ft
ft
ft
ft
ft
2.6
1.4
Cl
4.8
3.5
8.9
7.5
*
ft
14.2
ft
3.4
2.6
0.9
0.8
I/ Includes ammoniacal nitrogen
* Insufficient Sample
-------
Table A-26.
Chemical Composition of Sewage Effluent .Applied on
Original Forestry Experimental Plots (Faim Woodlot
Site) During the Period 4/5/66 to 11/15/66.
Constituent
Min
Range
Max
—' Includes ammoniacal nitrogen
Average
PH
MBAS
Nitrate-N
Organic-Mi/
Phosphorus
Potassium
Calcium
Magnesium
Sodium
Chloride
Boron
Manganese
mg/1
7.1
0.1
1.9
2.0
4.331
5.7
8.9
4.3
14.3
17.5
0.12
0.01
mg/1
8.2
1.5
20.3
12.2
17.161
31.8
44.4
31.9
49.1
87.4
0,80
0.18
mg/1
7.6
0.4
7.5
5.0
9.520
17.5
28.5
17.3
33.4
46.3
0.36
0.05
461
-------
Tabel A-27.
Average Concentration of Constituents in the Combined Effluent and Stoim Percolate
Samples of the Original Forestry Plots (Farm Woodlot Site) Druing the Irrigation
Period 4/5/66 to 11/15/66.
to
PH
MBAS
N03-N
Org-N^ P
K
Concentration
Effluent Quality
Hardwood 1-inch
Forest Floor Pans
6" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
Red Pine 1-inch
Forest Floor Pans
6" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
Red Pine 2- inch
Forest Floor Pans
6" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
Old Field 2 -inch
6" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
7.6
6.9
7.5
7.1
7.2
6.8
7.0
6.7
7.2
7.2
7.4
7.0
6.8
7.1
7.0
6.6
0.40
0.16
0.07
0.04
0.02
0.14
V
ff.04
0.09
0.21
I/
IT. 07
0.03
0.08
0.05
0.05
7.5
13.0
3.3
2.1
0.2
13.4
1.5
0.2
2.1
15.5
26.8
14.6
9.3
4.3
7.5
5.0
5.0 9.520
3.9 5.094
I/ 0.429
1.0 0.077
1.2 0.043
4.7 4.965
I/ 0.202
IT.8 0.024
0.9 0.134
4.1 7.996
I/ 0.373
U.7 0.049
1.3 0.143
I/ 0.091
T.4 0.069
1.4 0.140
17.5
17.3
10.7
6.6
5.6
15.8
I/
~6.9
9.5
18.4
I/
~6.7
5.8
I/
^.6
6.4
Ca
Mg
Na
Cl
Mn
B
in ing/liter
28.5
22.3
14.9
11.8
6.9
23.2
I/
"7.9
13.9
28.9
I/
T2.2
6.1
I/
8.6
2.2
17.3
9.2
10.5
8.0
7.0
9.8
I/
2.6
6.3
16.7
V
4.6
2.6
I/
~3.7
2.1
33.4
22.6
46.3
32.6
17.6
24.2
I/
17.7
12.8
33.8
V
T8.5
35.6
I/
19.6
31.1
46.3
28.7
37.1
64.9
40.5
32.2
46.0
48.4
15.1
44.9
88.1
103.5
65.0
43.4
45.4
49.4
0.05
0.17
0.07
0.03
0.07
0.04
I/
F.08
0.20
0.06
I/
IT. 07
0.16
I/
IT. 03
0.07
0.36
0.20
0.18
0.07
0.04
0.18
I/
F.04
0.12
0.28
I/
tf.06
0.06
I/
0~.12
0.10
i Insufficient sample volume for complete chemical analyses
—' Includes amnoniacal nitrogen
-------
Table A-28. Average Concentration of Constituents in the Percolate Samples of the Original
Forestry Control Plots (Farm Woodlot Site) During the Period 4/2/66 to 11/15/66.
pH
MBAS
N03-N
Org-N^/
P K
Concentration
Hardwood 1" Control
Forest Floor Pans
6" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
Red Pine Control Plots
Forest Floor Pans
1" Control
6" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
2" Control
6" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
Old Field 2" Control
6" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
6.3
7.1
7.3
6.7
6.4
6.9
6.9
6.8
7.0
6.7
6.5
6.9
6.9
6.7
0.09
0.04
0.03
0.03
0.11
0.00
0.01
0.01
0.05
0.03
0.02
0.03
0.08
0.03
7.1
0.1
0.1
0.1
6.9
0.1
0.0
0.0
0.1
0.3
0.2
0.1
0.4
0.1
4.0 .
2.4 .
1.3
1.3
4.4 .
*
*
5.1 .
0.7
A
*
1.7 .
0.6 .
•
•
0.9 .
569 11.5
048 11.4
034 7.6-
037 5.0
394 9.0
158 *•
053 2.4
062 5.7
156 *
074 3.3
022 3.9
038 16.2
030 *
030 10.0
Ca
Mg
Na
Cl
Mn
B
in mg/liter
17.0
14.0
19.2
6.7
18.1
*
7.0
2.2
*
11.4
2.5
15.8
*
3.5
1.7
3.4
16.9
6.3
1.7
*
2.5
1.1
*
3.1
0.8
2.8
*
1.1
1.2
3.4
2.4
6.0
1.5
A
3.5
1.4
*
3.3
3.0
2.8
*
8.4
1.6
4.1
1.6
2.0
1.7
1.7
2.6
2.4
1.6
10.4
5.2
1.3
2.1
0.5
0.16
0.08
0.05
0.07
0.10
*
0.12
0.03
*
0.28
0.05
0.04
*
0.05
0.08
0.12
0.05
0.04
0.06
*
0.06
0.04
*
0.02
0.03
0.02
*
0.06
* Insufficient sample for complete analyses
— Includes ammoniacal nitrogen
-------
Table A-29.
Chemical Composition of Sewage Effluent Applied on
Original Forestry Experimental Plots (Farm Woodlot
Site) During the Period 4/18/67 to 10/31/67.
Constituent
pH
MBAS
Nitrate -N
Organic-Nl/
Phosphorus
Potassium
Calcium
Magnesium
Sodium
Chloride
Boron
Manganese
Range
Min
mg/1
6.9
0.1
2.2
0.0
0.361
3.5
9.9
4.1
15.8
18.6
0.12
0.00
Max
mg/1
8.1
2.0
15.2
8.2
12.524
28.6
34.2
18.5
51.3
82.9
0.55
0.62
Average
mg/1
7.0
0.4
6.3
4.5
7.682
13.9
20.3
10.6
35.4
46.8
0.34
0.06
— Includes ammoniacal nitrogen.
464
-------
Table A-30.
Average Concentration of Constituents in the Combined Effluent and Storm Percolate
Samples of the Original Forestry Plots (Farm Woodlot Site) During the Irrigation
Period 4/18/67 to 10/31/67.
tn
pH MBAS NCyN Org-N^ Cl
Na
Ca
Mg Mn B
Effluent Quality
7.0 0.45
6.3
Concentration in mg/liter
4.5 46.8 7.682 35.4 13.9
20.3 10.6 0.06 0.34
Hardwood 1-inch
Forest Floor Pan
6" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
Red Pine 1-inch
Forest Floor Pan
6" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
Red Pine 2 -inch
Forest Floor Pan
6" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
Old Field 2 -inch
6" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
7.0
7.5
7.1
7.0
6.8
7.6
7.1
7.5
7.0
7.2
6.9
6.5
7.6
7.4
6.8
0.18
0.12
0.10
0.13
0.16
0.11
0.09
0.05
0.18
0.10
0.08
0.08
0.09
0.05
0.06
10.9
13.3
5.4
1.4
11.3
6.9
5.1
1.7
14.7
9.6
10.6
13.8
4.6
12.0
6.1
3.2
1.7
0.8
0.9
3.4
2.0
2.9
2.3
3.4
2.0
1.0
1.1
2.8
1.1
0.8
22.1
14.1
45.4
64.8
21.3
26.7
43.3
35.8
40.0
70.3
78.1
87.8
33.9
33.7
42.5
4.651
0.068
0.078
0.077
3.851
0.149
0.108
0.092
6.987
0.242
0.072
0.031
0.136
0.097
0.068
18.2
35.2
40.9
25.6
18.3
22.2
27.7
17.2
26.1
41.0
54.5
45.5
32.4
42.4
34.7
13.8
7.8
5.9
5.9
12.4
12.1
9.4
7.6
12.9
18.7
5.7
4.9
9.2
7.7
6.0
18.9
33.2
6.7
4.9
18.7
30.6
27.0
29.7
23.8
24.3
5.6
1.8
27.1
20.1
1.1
7.4
28.4
5.0
5.1
29.1
26.2
14.9
17.8
11.2
22.2
3.0
1.7
15.4
14.0
1.1
0.16
0.07
0.10
0.06
0.05
0.04
0.05
0.10
0.12
1.59
0.04
0.09
0.10
0.03
0.03
0.19
0.31
0.16
0.04
0.16
0.22
0.13
0.12
0.26
0.40
0.08
0.04
0.33
0.21
0.17
I/
Includes ammoniacal nitrogen
-------
CTv
Table A-31. Average Concentration of Constituents in the Percolate Samples of the Original
Forestry Control Plots (Farm Woodlot Site) During the Period 4/18/67 to 10/31/67.
pH
MBAS
N03-N
Org-N^
Cl
P
Concentration in
Hardwood 1" Control
Forest Floor Pans 6.3
6" Tension Lysimeter 7.6
24" Tension Lysimeter 7.3
48" Tension Lysimeter 7.1
Red Pine Control Plots
Forest Floor Pans 7.5
1" Control
6" Tension Lysimeter 7.6
24" Tension Lysimeter 7.6
48" Tension Lysimeter 7.2
2" Control
6" Tension Lysimeter 7.1
24" Tension Lysimeter 7.1
48" Tension Lysimeter 6.7
Old Field 2" Control
6" Tension Lysimeter 7.2
24" Tension Lysimeter 7.2
48" Tension Lysimeter 6.9
0.12
0.09
0.09
0.09
0.14
0.14
0.08
0.08
0.05
0.09
0.06
0.15
0.09
0.07
5.0
0.4
0.4
0.3
6.0
0.6
0.2
0.1
1.3
0.7
1.8
0.4
0.4
0.3
3.3
1.7
1.5
1.5
4.0
2.4
0.7
1.0
I/
1.1
1.5
1.9
0.9
1.0
0.9
2.3
2.1
2.5
1.0
1.9
4.7
1.3
8.0
15.5
6.1
1.3
1.7
0.7
0.818
0.053
0.030
0.044
0.477
0.052
0.056
0.051
0.079
0.024
0.056
0.045
0.032
0.039
Na
K
Ca
Mg
Mn
B
mg/liter
1.6
3.8
3.0
9.5
2.8
3.9
2.2
1.4
7.0
6.0
5.1
1.9
1.2
1.4
10.3
14.2
7.4
6.0
9.3
11.9
6.8
1.8
7.8
5.7
5.1
7.2
8.9
5.4
11.6
46.9
16.3
11.2
13.7
35.5
32.9
3.3
23.5
18.2
5.6
14.6
8.2
1.3
1.3
34.2
12.5
10.9
1.8
20.8
19.5
1.4
12.5
8.5
2.6
5.1
3.6
0.6
0.06
0.10
0.21
0.13
0.13
0.07
0.03
0.02
0.73
0.07
0.06
0.03
0.03
0.04
0.34
0.12
0.05
0.05
0.06
0.10
0.05
0.03
0.12
0.04
0.04
0.05
0.04
0.04
—' Insufficient samples volume for complete analyses.
2/
— Includes ammoniacal nitrogen.
-------
Table A-32.
Chemical Composition of Sewage Effluent Applied on
Original Forestry Experimental Plots (Farm Woodlot
Site) During the Period 4/9/68 to 11/12/68.
Constituent
pH
MRAS
Nitrate-N
Organic-Ni/
Phosphorus
Potassium
Calcium
Magnesium
Sodium
Chloride
Boron
Manganese
NH4-N
Range
Min
ppm
6.3
0.0
0.0
2.5
2.015
12.1
17.9
8.9
27.4
16.7
0.23
0.03
4.5
Max
ppm
8.1
2.4
12.6
38.5
16.193
23.8
33.4
17.0
65.6
77.1
0.69
0.20
25.5
Average
ppm
7.7
0.6
5.1
19.9
8.455
18.6
26.4
13.3
40.2
46.4
0.37
0.12
13.2
Includes ammoniacal nitrogen.
467
-------
-Table A-33. Average Concentration in Percolate Samples and in the Sewage Effluent for the Original
Forestry Plots (Farm Woodlot Site) During the Irrigation Period 4/9/68 to 11/12/68.
oo
pH MBAS NO--N NH.-N
Cl
Na
K
Ca
Mg Mn B
Effluent Quality
Hardwood 1-inch
Forest Floor Pans
6" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
Red Pine 1-inch
Forest Floor Pans
6" Tension Lysimeter
12" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
Red Pine 2-inch
Forest Floor Pans
6" Tension Lysimeter
12" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
7.7 0.59 5.1 13.2
7.
7.
7.
8.
7.
7.
7.
7.
7.
7.
7.
7.
7.
6.
1
5
1
0
1
5
9
8
6
5
3
8
1
8
0.
0.
I/
I/
0.
0.
0.
V
I/
0.
0.
I/
T/
IT.
17
7
17
08
08
17
15
11
14.
10.
10.
8.
15.
18.
19.
6.
2.
15.
21.
32.
17.
19.
8
9
0
0
9
7
8
1
7
8
8
7
6
9
4.
1.
3.
3.
5.
1.
1.
0.
0.
5.
1.
3.
0.
0.
6
4
0
0
2
3
3
6
7
5
6
0
7
6
Concentration in mg/liter
19.9 46.4 8.455 40.2 18.6 26.4 13.3 0.12
7.0
2.3
1.7
3.6
2.0
8.0
2.2
2.5
0.7
0.8
0.37
32.6
51.9
70.2
38.6
33.1
46.0
37.9
35.9
53.0
42.0
49.2
72.9
88.2
88.5
6.
0.
0.
0.
6.
0.
0.
0.
0.
7.
1.
0.
0.
0.
808
166
388
222
501
562
262
253
089
678
007
134
109
044
27.
38.
I/
T/
27.
39.
40.
36.
28.
33.
42.
52.
57.
61.
4
6
5
8
2
7
7
5
2
6
7
1
18.
10.
I/
T/
14.
11.
15.
7.
6.
16.
16.
34.
5.
5.
5
3
0
4
3
6
6
3
9
0
7
1
25.
30.
I/
11
25.
40.
74.
28.
35.
26.
36.
98.
17.
6.
6
8
1
7
5
9
9
2
7
6
5
9
10.3
25.7
V
I/
10.0
30.3
30.1
15.8
25.6
11.8
22.9
54.8
7.5
3.9
0.11
0.03
I/
I/
0.10
0.03
0.06
0.02
0.03
0.19
0.14
0.46
0.06
0.07
0.23
0.28
I/
I/
0.20
0.27
0.20
0.20
0.09
0.24
0.32
0.32
0.24
0.12
-------
Table A-33. Continued.
pH MBAS N03-N NH4~N Org-N?/ Gl P Na K Ca Mg Mn B
Concentration
Old Field 2 -inch
6" Tension Lysimeter
12" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
7.5
8.0
7.8
7.4
0.21
I/
T/
17.16
4.8
6.1
4.9
3.7
0.8
1.0
1.1
0.7
1.6
1.5
2.1
1.4
32.9
46.4
35.3
30.9
0.275
0.073
0.125
0.053
in mg/liter
28.3
43.1
29.2
30.2
2.4
12.6
7.0
4.0
22.8
53.1
42.9
11.4
13.3
34.4
25.9
7.7
0.03
0.03
0.03
0.38
0.26
0.27
0.27
0.18
— insufficient sample volume for complete chemical analyses.
2/
— Includes ammoniacal nitrogen.
-------
--4
O
Table A-34. Average Concentration of Constituents in the Percolate Samples of the Original Forestry
Control Plots (Farm Woodlot Site) During the Period 4/9/68 to 11/12/68.
pH MBAS
N03-N
NH4-N
Org-N-/
Cl
P
Concentration
Hardwood 1" Control
Forest Floor Pans 6.7 0.11
6" Tension Lysimeter 7.6 0.12
24" Tension Lysimeter 7.4 0.09
48" Tension Lysimeter 7.1 0.21
Red Pine Control
Forest Floor Pans 6.6 0.12
1" Control
6" Tension Lysimeter 7.9 0.08
24" Tension Lysimeter 7.8 0.05
48" Tension Lysimeter 7.5 0.07
2" Control
48" Tension Lysimeter 6.9 0.06
Old Field 2" Control
24" Tension Lysimeter 6.5 0.04
48" Tension Lysimeter 6.9 0.11
6.8
0.4
0.2
0.1
8.6
0.5
0.2
0.2
1.6
0.2
0.2
2.4
0.9
0.5
3.3
2.7
1.1
0.9
0.6
0.1
0.5
0.4
4.7
1.4
0.9
4.0
5.0
1.0
0.6
0.3
0.5
0.8
0.6
1.7
2.8
1.8
2.5
1.7
0.2
1.1
0.4
13.7
1.0
1.4
0.773
0.064
0.044
0.106
0.762
0.024
0.013
0.134
0.015
0.122
0.040
Na
in ppm
0.7
1.1
2.7
6.3
0.7
2.0
I/
1.7
11.9
1.8
1.5
K
10.5
2.3
3.6
5.1
7.7
5.8
I/
~2.0
5.4
0.4
3.2
Ca
16.4
20.9
12.8
8.8
18.4
21.0
I/
"3.0
3.5
7.5
1.9
Mg
1.4
13.7
10.0
7.5
1.6
9.4
I/
1.2
0.9
2.3
0.5
Mn
0.08
0.05
0.13
0.49
0.06
0.04
V
zr.03
0.02
0.01
0.01
B
0.06
0.03
0.03
0.04
0.05
0.06
V
0~.02
0.04
0.02
0.03
— Insufficient sample^volume for complete chemical analyses.
2/
—' Includes ammoniacal nitrogen.
-------
Table A-35. Average Concentration of Percolate Samples and of Sewage Effluent in the New Red
Pine - 2 inches Per Week Area. 1965 and 1966.
Effluent Quality
6" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
PH
7.7
7.7
6.8
7.0
MBAS
1.07
.07
0.10
.08
N03-N
Org-N=-' P K Ca
Concentration in mg/1
Irrigation Period - 4/20/65
6.2 2.8 10.129 15.2
13.8 0.8 1.452 10.7
11.0 0.7 .823 6.9
14.5 0.3 .834 6.0
Irrigation Period - 4/5/66
Effluent Quality
Forest Floor Pans
6" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
7.7
7.3
6.7
6.8
6.8
0.38
0.228
0.06
0.07
0.07
6.0
13.9
18.6
14.7
8.9
4.9
3.9
1.1
1.3
1.2
9.383
8.102
.076
.064
.058
17.0
16.3
11.7
5.3
6.6
Mg
Na
to 11/16/65
29.7 15.3 35.8
23.2 5.0 36.3
16.1 3.8 28.9
11.9 2.1 17.0
Cl
47.2
52.8
45.8
30.9
Mn B
to 11/15/66
29.2
27.7
14.2
13.2
8.8
16.9
15.1
6.8
5.6
4.0
34.7
34.2
34.6
32.6
22.2
51.2
50.0
53.8
50.2
32.2
0.06 0.33
0.07 0.26
0.26 0.20
0,22 0.10
0.26 0.10
— Includes ammoniacal nitrogen.
-------
Table A-36.
Average Concentration in Percolate Samples and in Sewage Effluent for the New Red
Pine - 2 inches Per Week Area. 1967 and 1968.
-4
to
pH MBAS N03-N NH4~N Org-N^/ P K Ca Mg
Concentration in mg/1
Na Cl Mn B
Irrigation Period - 4/18/67 to 10/31/67
7.7 0.47 4.9 - 4.1 8/721 14.6 21.6 11.2 36.7 45.4 0.10 0.41
Effluent Quality
6" Tension Lysimeter
24" Tension Lysimeter
48". Tension Lysimeter
Effluent Quality
6" Tension Lysimeter
12" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
6.3 0.08 16.7
6.5 0.09 14.5
6.5 0.09 11.1
1.1 0.132 11.2 12.1 8.4 33.1 37.4 0.19 0.19
1.2 0.049 6.0 8.7 4.2 34.6 43.9 0.09 0.10
1.7 0.163 8.2 4.9 3.2 24.0 30.2 0.13 0.11
Irrigation Period - 4/9/68 to 11/12/68
7.8 0.38 3.6 17.2 22.1 9.656 16.4 25.6 12.9 41.3 46.0 0.15 0.35
7.5 0.07 23.9 1.3 1.6
8.0 0.02 24.6 1,5 1.5
7.6 0.11 21.3 1.0 1.4
7.0 0.07 16.1 1.1 1.1
0.609 13.7 51.6 32.6 42.3 42.8 0.17 0.26
0.384 12.8 73.5 36.1 43.6 43.2 0.15 0.22
0.131 10.4 57.1 32.1 48.4 41.3 0.06 0.21
0.247 8.1 13.0 9.1 37.0 34.4 0.23 0.17
— Includes aranoniacal nitrogen.
-------
Table A-37.
'Average Concentration of Percolate Samples and of the Sewage Effluent in the New
Gamelands Area. 1966 and 1967.
pH
Effluent Quality 7. 7
Forest Floor Pans 7.1
6" Tension Lysiraeter 7.1
24" Tension Lysimeter 6.8
48" Tension Lysimeter 6.6
Effluent Quality 7.6
Forest Floor Pans 7.2
6" Tension Lysimeter 7.0
24" Tension Lysimeter 6.2
48" Tension Lysimeter 6.4
MBAS
0.55
0.19
0.08
0.06
0.06
0.36
0.18
0.10
0.08
0.09
N03-N Org-N-/ P K
Concentration
5.8
15.4
12.5
14.9
10.6
5.7
14.9
16.9
20.4
19.2
Irrigation
4.0
4.2
1.8
1.3
1.2
Irrigation
4.6
2.9
2/
T.6
1.4
Period
9.779
7.241
0.248
0.029
0.041
Period
8.435
7.287
0.113
0.057
0.063
Ca Mg
in mg/1
Na
Cl
Mn
B
- 5/18/66 to 12/26/66
18.4
17.8
17.9
8.6
9.4
32.8
"24.4
11.1
12.3
10.8
- 1/2/67 to
14.9
15.3
11.0
11.2
6.7
22.0
22.8
14.9
20.4
18.4
18.9
21.8
8.1
3.1
5.2
38.2
32.5
36.0
37.7
28.9
51.5
43.4
53.1
49.6
51.1
0.08
0.12
0.63
1.19
1.11
0.35
0.24
0.14
0.16
0.10
12/25/67
11.2
9.8
7.7
13.7
11.6
36.4
19.0
31.5
31.7
34.1
48.1
36.8
41.1
41.7
42.5
0.13
0.19
0.13
0.26
0.48
0.34
0.25
0.22
0.17
0.16
—' Includes ammoniacal nitrogen.
2/
— Insufficient samples.
-------
45-
--J
Table A-38. Average Concentration of Percolate in the Hardwood Control Plot at the New Gamelands
Site. 1966 and 1967.
Forest Floor Pans
6" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
6" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
pH
6.4
6.8
7.2
6.8
6.7
7.5
6.8
MBAS
0.11
0.02
0.03
0.03
0.08
0.03
0.07
N03-N
8.5
0.2
0.5
0.1
10.6
0.5
1.4
Org-N^/ P K Ca Mg
Concentration in mg/1
4.6
1.5
1.0
1.5
2/
r.o
1.1
0.590
0.076
0.091
0.058
0.049
0.223
0.068
1966
10.5
5.8
6.2
6.4
1967
5.1
10.2
7.0
19.8
11.1
13.6
8.0
9.2
4.7
3.2
1.7
1.7
3.3
4.9
2.7
21.5
4.6
Na
1.1
1.3
6.7
2.2
1.4
1.5
4.0
Cl
1.6
1.3
2.4
13.7
1.1
0.8
7.7
Mn
0.23
0.30
0.05
0.18
0.42
0.24
0.06
B
0.06
0.03
0.05
0.04
0.04
0.07
0.04
— Includes ammoniacal nitrogen.
2/
— Insufficient samples.
-------
Table A-39.
Average Concentration in Percolate Samples and Sewage Effluent for the Hardwoods
New Gamelands Area which Received 2 Inches of Effluent Per Week During the Period
1/1/68 to 12/31/68 and for a Nearby Control Area.
pH MBAS N03-N
NH4-N Org-N^
/ Cl P Na K
Concentration - mg/1
Ca
Mg
Mn
B
Irrigated Area
Effluent Quality
Forest Floor Pans
6" Tension Lysimeter
12" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
7.7 0.56 4.2
7.3 0.33 13.5
7.3 0.10 22.3
7.8 0.06 21.9
6.7 0.09 26.0
7.1 0.11 25.9
16.8
10.0
1.3
2.9
0.9
1.0
20.9
13.6
2.0
3.1
1.3
1.2
49.5
47.3
46.8
43.2
45.7
49.5
9.081
8.997
0.452
2.955
0.129
0.116
42.6
40.4
38.6
37.0
37.9
37.7
14.9
15.4
11.8
11.7
8.5
11.0
24.3
26.0
41.7
48.6
25.4
26.3
11.8
11.9
22.7
27.9
15.1
14.1
0.19
0.25
0.08
0.12
0.13
0.63
0.33
0.28
0.25
0.23
0.17
0.19
Control Area
Forest Floor Pans
6" Tension Lysimeter
12" Tension Lysimeter
24" Tension Lysimeter
48" Tension Lysimeter
6.9 0.13 6.9
6.9 0.07 0.1
8.1 2/ 0.2
6.8 0.20 0.2
6.8 0.08 0.1
2.8
0.4
0.9
0.1
0.3
5.6
1.2
1.4
1.7
1.1
1.8
1.9
5.8
0.6
1.2
0.725
0.020
0.041
0.050
0.071
1.4
1.0
2.0
1.3
2.8
8.6
3.3
5.2
5.6
4.6
17.1
11.7
28.6
14.0
6.4
1.4
5.1
16.8
2.1
3.0
0.71
0.66
0.13
0.07
0.03
0.05
0.04
0.05
0.06
0.03
— Includes anrmoniacal nitrogen.
21
— Not analyzed.
-------
Table A-40. Average Concentration of Constituents in the Effluent and in the Percolate at Various
Soil Depths on the Plot which Received 4 Inches Per Week During 1965.
Soil
depth
inches
Effluent Quality
6
12
24
26
48
60
72
MBAS
Concn
mg/1
1.61
0.35
0.27
0.23
0.20
0.16
0.16
0.23
Nitrate
N
Concn
mg/1
7.6
7.3
5.7
4.2
5.3
2.3
4.8
5.2
Organic—
N
Concn
mg/1
2.7
1.2
1.5
1.1
1.1
1.1
0.8
0.9
P
Concn
mg/1
10.383
2.053
1.311
1.471
1.441
1.700
1.480
1.621
K
Concn
mg/1
16.3
13.1
7.6
8.4
7.9
6.6
7.2
7.5
Ca
Concn
mg/1
29.5
17.5
6.5
6.2
5.2
8.9
8.3
3.7
Mg
Concn
mg/1
14.8
12.6
4.7
2.5
5.2
6.3
4.9
2.2
— Includes ammoniacal nitrogen.
-------
Table A-41. Average Concentration of Constituents in the Percolate Samples Collected from Pan
Lysimeters Located in the Hardwood Plot which Received 4 Inches of Effluent Per Week
During the Period 4/5/66 to 11/17/66
pH
MBAS
N03-N
Org-N^/
P
K Ca
Concentration
Effluent Quality
Soil Depth - inches
6
12
24
26
48
60
72
7.6
7.5
7.1
6.9
6.9
7.0
7.0
6.9
0.40
0.40
0.16
0.11
0.08
0.09
0.08
0.12
7.5
11.1
9.0
9.3
9.1
9.1
11.1
9.5
5.0
2.7
2.3
1.6
1.3
1.1
1.0
1.0
9.520
5.347
0.816
0.193
0.044
0.018
0.040
0.047
17.5 28.5
14.7 26.1
10.6 12.3
7.7 6.5
7.5 5.1
6.3 10.6
6.3 6.9
5.2 3.4
Mg
in mg/1
17.3
17.9
11.6
3.3
5.4
6.8
4.1
2.0
Na
33.4
34.0
41.5
38.3
42.5
37.1
44.0
36.5
Cl
46.3
40.4
65.5
67.8
79.5
86.1
91.2
82.1
Mn
0.05
0.12
0.09
0.19
0.13
0.03
0.10
0.07
B
0.36
0.28
0.29
0.24
0.20
0.08
0.08
0.07
— Includes ammoniacal nitrogen.
-------
00
Table A-42. Average Concentration of Constituents in the Percolate Samples Collected from-Pan
Lysimeters. Located in the Hardwood Plot Which Received 4 Inches of Effluent Per Week
During the Period 4/18/67 to 10/31/67
pH MBAS
N03-N
Org-N^
Cl
P
Na
Concentration in
Effluent Quality
Soil Depth - inches
6
12
24
36
48
60
72
7.0 0.45
7.2 0.21
7.1 0.17
6,9 0.10
6.8 0.11
7.3 0.11
7.1 0.12
6.9 0.10
6.3
8.6
7.9
5.1
9.0
3.4
7.8
8.3
4.5
2.6
2.7
1.4
1.4
1.7
1.3
1.3
46.8
35.9
47.8
54.1
65.2
66.6
69. 6;
56.9
7.682
4.043
2.430
0.124
0.062
0.219
0.793
0.072
35.4
31.2
37.7
38.2
41.7
43.6
40.8
39.3
K
mg/1
13.9
14.4
12.8
6.9
7.0
4.4
5.2
6.9
Ca
20.3
21.8
16.4
5.8
5.5
16.6
6.8
2.5
Mg
10.6
12.3
12.6
3.8
6.3
8.6
3.9
1.8
Mn
0.06
0.13
0.10
0.20
0.18
0.03
0.15
0.00
B
0.34
0.27
0.30
0.28
0.24
0.13
0.12
0.13
— Includes ammoniacal nitrogen.
-------
Table A-43.
Mean Nutrient Element Concentration of the Soil Samples
Collected in 1963, 1964, and 1965 in the Red Pine 1-inch
Treatment and Control Plots
Depth N Cl
K
Ca
Mg
Mn B
Na
1 mg/1 me/lOOgm me/lOOgm me/lOOgm mg/1 mg/1 me/lOOgm
TREATMENT
1963
1.0
2.0
3.0
4.0
5.0
1964
0.5
1.0
2.0
3.0
1965
0.5
1.0
2.0
3.0
4.0
5.0
(Fall)
0.088
0.021
0.014
0.014
0.010
(Spring)
0.094
0.032
0.026
0.024
(Fall)
0.121
0.075
0.030
0.019
0.026
0.013
10.5
24.4
15.5
20.8
10.1
50.7
10.5
68.3
49.7
20.1
27.5
22.1
18.4
13.5
.1.7
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
51
34
42
52
59
21
31
29
37
79
71
73
99
76
94
1.2
1.9
1.3
1
0
0
1
1
0
2
1
2
2
2
1
.0
.7
.7
.2
.7
.8
.3
.4
.2
.5
.2
.5
0.5
0.7
0.7
0.9
0
0
0
0
0
1
0
0
1
2
1
.7
.3
.2
.7
.7
.0
.4
.8
.8
.3
.7
122
48
48
54
46
172
88
54
42
18
17
9
3
4
6
0.4
0.2
0.6
0.4
0.6
0.4
0.4
0.4
0.4
1.0
1.0
1.0
1.0
0.8
1.2
0.29
0.12
0.12
0.14
0.14
0.22
0.25
0.21
0.11
0.45
0.48
0.39
0.29
0.25
0.18
CONTROL
1963
1.0
2.0
3.0
4.0
5.0
1964
0.5
1.0
2.0
3.0
(Fall)
0.07
0.017
0.014
0.014
0.008
(Spring)
0.103
0.042
0.023
0.020
12.7
4.7
8.6
9.8
2.8
8.6
13.3
8.2
6.6
0.
0.
0.
0.
0.
29
45
42
42
51
0.45
0.
45
0.51
0.39
1
2
0
0
0
0
0
1
0
.3
.0
.9
.9
.8
.7
.8
.4
.8
0
0
1
1
1
0
0
0
1
.2
.7
.1
.4
.4
.2
.2
.8
.2
126
36
48
36
42
198
78
31
38
0.2
0.4
0.4
0.6
0.4
0.4
0.6
0.4
0.4
0.17
0.13
0.10
0.16
0.12
0.19
0.10
0.14
0.15
479
-------
Table A-43. Continued.
Depth N Cl K Ca Mg Mn B Na
% mg/1 me/lOOgm me/lOOgm me/lOOgm mg/1 mg/1 me/lOOgm
1965 (Fall)
0.5 0.148 13.8 0.53 2.1 0.2 34 0.6 0.19
1.0 0.079 10.1 0.47 1.6 0.3 21 0.6 0.12
2.0 0.024 21.7 0.64 3.5 1.0 8 0.8 0.19
3.0 0,016 22.5 0.61 1.3 0.9 8 0.8 0.18
4.0 0.018 17.8 0.61 0.8 1.1 10 0.6 0.18
5.0 0.018 6.2 0.67 0.8 1.1 10 0.8 0.12
480
-------
Table A-44.
Mean Chemical Element Concentration of the Soil Samples
Collected in 1963, 1964, and 1965 in the Red Pine 2-inch
Treatment and Control Plots.
Depth
N
Cl
K
Ca
Mg
Mn
B
Na
% mg/1 me/lOOgm me/lOOgm me/lOOgm mg/1 mg/1 me/lOOgm
1963 (Fall)
1.0
2.0
3.0
4.0
5.0
1964
0.5
1.0
2.0
3.0
1965
0.5
1.0
2.0
3.0
4.0
5.0
1963
1.0
2.0
3.0
4.0
5.0
1964
0.5
1.0
2.0
3.0
0.070
0.031
0.023
0.028
0.026
(Spring)
0.168
0.053
0.025
0.068
(Fall)
0.128
0.059
0.030
0.025
0.018
0.019
(Fall)
0.075
0.026
0.019
0.020
0.015
(Spring)
0.115
0.084
0.034
0.020
12.4
29.1
39.6
19.2
16.9
13.9
53.9
21.8
30.5
12.6
18.8
20.6
23.9
29.1
30.7
4.2
4.3
4.1
5.2
11.8
31.7
14.8
43.9
9.3
0.42
0.47
0.53
0.67
0.51
0.88
0.56
0.45
0.37
0.34
0.39
0.39
0.29
0.29
0.29
0.42
TREATMENT
1.3
2.2
1.3
1.2
1.1
0.4
0.8
1.4
1.4
1.8
13.9
53.9
21.8
30.5
0.79
0.96
0.39
0.34
4.4
1.3
1.6
1.1
1.6
0.4
0.6
0.9
86
96
66
50
0.8
0.6
0.4
0.4
0.31
0.23
0.30
0.27
3.8
1.3
2.1
1.5
0.9
0.9
CONTROL
1.2
2.2
0.9
0.5
0.3
1.8
0.7
0.5
0.9
1.0
1.1
0.3
0.
0.
0.6
0.4
31.7
14.8
43.9
9.3
0.42
0.45
0.39
0.50
0.9
1.5
1.9
1.1
0.2
0.2
0.6
1.0
196
74
46
48
0.4
0.6
0.6
0.6
0.09
0.20
0.16
0.15
80
42
48
42
56
86
96
66
50
17
19
10
14
9
10
98
40
32
34
26
196
74
46
48
0.6
0.6
0.6
0.4
0.4
0.8
0.6
0.4
0.4
1.0
0.8
0.6
0.6
0.4
0.6
0.6
0.6
0.4
0.4
0.6
0.4
0.6
0.6
0.6
0.31
0.28
0.17
0.15
0.12
0.45
0.43
0.44
0.50
0.41
0.39
0.14
0.17
0.14
0,16
0.09
481
-------
Table A-44. Continued.
Depth N Cl K Ca Mg Mn B Na
\ mg/1 me/lOOgm me/lOOgm me/lOOgm mg/1 mg/1 me/lOOgm
1965 (Fall)
0.5
1.0
2.0
3.0
4.0
5.0
0.122
0.045
0.023
0.018
0.020
0.012
9.7
7.3
12.3
14.7
22.5
15.4
0.
0.
0.
0.
0.
0.
64
54
62
53
53
51
1
1
1
0
0
0
.7
.9
.6
.6
.4
.4
0.
0.
0.
0.
0.
0.
2
5
9
7
6
5
44
18
22
16
16
30
0.8
0.6
0.8
0.6
0.8
0.8
0.16
0.16
0.17
0.12
0.15
0.22
482
-------
Tabie A-45.
Mean Nutrient Element Concentration of the Soil Samples
Collected in 1963, 1964, 1965 in the Open Area 2-inch
Treatment and Control Plots.
Depth
N
Cl
K
Ca
Mg
Mn
B
Na
I mg/1 me/lOOgm me/lOOgm me/lOOgm mg/1 mg/1 me/lOOgm
1963 (Fall)
1.0
2.0
3.0
4.0
5.0
1964
0.5
1.0
2.0
3.0
1965
0.5
1.0
2.0
3.0
.4.0
5.0
1963
1.0
2.0
3.0
4.0
5.0
*
1964
0.5
1.0
2.0
3.0
0.072
0.022
0.017
0.014
0.016
(Spring)
0.118
0.053
0.025
0.019
(Fall)
0.149
0.048
0.021
0.016
0.016
0.013
(Fall)
0.088
0.016
0.012
0.010
0.010
(Spring)
0.130
0.057
0.051
0.025
27.6
30.6
16.5
17.7
17.8
21.9
18.0
49.7
33.9
13.2
9.9
20.3
23.0
18.8
13.9
7.7
2.6
2.3
7.5
9.6
13.5
4.2
19-1
11.7
0.64
0.62
0.64
0.56
0.51
0.97
0.53
0.47
0.56
0.47
0.56
0.37
0.51
0.51
0.45
0.45
0.37
0.37
0.29
0.29
TREATMENT
1.7
1.8
1.0
0.8
0.6
0.5
0.9
0.9
0.9
0.8
21.9
18.0
49.7
33.9
0.53
0.19
0.31
0.26
2.1
1.6
1.5
0.8
0.6
0.5
0.7
0.7
78
50
42
38
0.4
0.2
0.2
0.2
0.24
0.28
0.29
0.25
3.7
1.3
2.2
1.7
1.2
0.7
CONTROL
1.4
1.9
1.1
0.9
0.9
1.3
1.5
1.9
0.8
1.4
0.5
0.8
1.1
1.0
0.6
0.3
0.8
1.3
1.6
1.5
0.3
0.3
0.9
1.0
44
20
26
62
18
78
50
42
38
6
6
5
5
5
5
72
20
22
18
18
74
44
22
44
1.0
0.8
0.8
0.8
0.8
0.4
0.2
0.2
0.2
1.0
1.0
0.6
0.8
0.6
1.0
0.6
0.6
0.6
0.6
0.6
0.4
0.4
0.2
0.2
0.25
0.22
0.10
0.09
0.09
0.35
0.30
0.43
0.29
0.28
0.27
0.09
0.14
0.19
0.18
0.16
0.19
0.11
0.20
0.17
483
-------
Table A-45. Continued.
Depth N Cl K Ca Mg Mn B Na
% mg/1 me/lOOgm me/lOOgm me/lOOgm mg/1 mg/1 me/lOOgm
1965 (Fall)
0.5
1.0
2.0
3.0
4.0
5.0
0.107
0.048
0.028
0.018
0.018
0.014
1.5
2.8
7.9
15.2
7.1
11.4
0.62
0.62
0.42
0.53
0.51
0.59
0.8
1.5
1.5
0.7
0.7
0.7
0.3
0.3
0.5
0.5
0.4
0.4
9
6
6
8
6
5
0.8
0.8
0.4
0.8
0.8
0.8
0.13
0.13
0.13
0.13
0.14
0.09
484
-------
B, Wells and Springs in Centre County Sampled by the Project
No, Name Location
1 Earl Tressler
2 Kermit Rockey
3 Robert Snetsinger
4 Bernard Crust
5 William Spearly
6 Harry Spearly
7 Basil Frank
8 Walter Richner
9 Edith Taylor
10 John Blair
11 Clarence Zeigler
12 Jerald Duck
13 Dennis Riordan
14 Steven Williams
15 John W. 'Myers
16 Kenneth Watson
17 Ralph E. Myers
18 Lake Wall
19 James Wilson
20 Charles Sellers
21 John Hokanson
22 James Bruss
23 Adolph Reed
24 Wayne Showers
25 Charles Stem
26 Benjamin Heim
27 Allen Wolford
28 Clifford Quick
29 William Hersh
30 Briarly Manor
31 Lester Myers, Jr.
32 Andrew Lentvorsky
33 Robert Delafield
34 Joseph Stover
35 Wayne Burnett
36 W. E. Clark, Jr.
37 Franklin King
38 David Araraerman
39 Robert Keith
40 Charles Taylor
41 Marvin Swatsworth
1935 Merle L. Wilson
1936 Raymond Fetzer
1937 Martin W. Schein
R. D. 1, Belief onte
R. D. 1, Belief onte
R. D. 1, Bellefonte
R. D. 1, Bellefonte
R. D. 1, Bellefonte
R. D, 1, Bellefonte
R. D. 1, Bellefonte
R. D. 1, Bellefonte
R. D. 1, Bellefonte
R. D. 1, Bellefonte
R. D. 1, Bellefonte
R. D. 1, Bellefonte
R. D. 1, Bellefonte
Port Matilda, R. D.
Port Matilda, R. D.
Port Matilda, R. D.
Port Matilda, R. D.
Port Matilda, R. D.
Port Matilda, R. D.
Port Matilda, R. D.
R. D. 1, Bellefonte
R. D. 1, Bellefonte
Port Matilda, R. D.
Port Matilda, R. D.
Port Matilda, R. D.
R. D. 1, Bellefonte
Houserville Rd., State College
Box 41, Lemont
Big Hollow Rd., State College
R. D. 1, Bellefonte
Port Matilda, R. D.
Port Matilda, R. D.
Rock Rd., State College
R. D. 1, Bellefonte
Puddintown Rd., State College
Box 556, State College
Port Matilda, R. D.
R. D. 1, Bellefonte
Big Hollow Rd., State College
R. D. 1, Bellefonte
Big Hollow Rd., State College
R. D. 1, Bellefonte
R. D. 1, Bellefonte
Rock Rd., State College
485
-------
No,
Name
Location
Sp.
Sp,
Sp.
Sp.
Sp.
Sp.
Un.
Un.
Un. 14
Un. 16
Un. 17
Un. 24
Un. 26
St. 1
Thoinpson Spring
Bathgate Spring
Musser Spring
Benner Spring
Paradise Spring
Big Spring
Penn State Univ.
Penn State Univ.
Penn State Univ.
Penn State Univ.
Penn State Univ.
Penn State Univ.
Penn State Univ.
Buffalo Run Stream
State College
Lemont Water Supply
Port Matilda, R. D.
Pa. Fish Hatchery
Pa. Fish Hatchery
Bellefonte Water Supply
University Park
University Park
University Park
University Park
University Park
University Park
University Park
Benner Township
486
-------
C. Chemical Procedures Used in Wastewater Project
EFFLUENT AND WATER SAMPLES
Organic Nitrogen (includes
Procedure:
Transfer an aliquot of the sample (50 ml. <10 ppm Mty-N; 10 ml -
to 60 ppm NH4-N) into a 125 ml. erlenmeyer flask. Add 5 ml. of sulfuric
acid-selenium oxychloride solution and swirl. Heat gradually to boiling
on a hot plate under a hood and digest until clear. Cool. If the solu-
tion is not colorless add 2 drops of 101 perchloric acid and shake
immediately. Heat again until colorless but do not boil. Cool. Trans-
fer to a 100 ml. volumetric flask and make up to volume. Shake flask
and transfer 10 ml, to a 50 ml. volumetric flask. Neutralize with
NaOH (approximately 2 ml. of 9N NaOH). Shake, add 2 ml. gum arabic,
make up to 35 to 40 ml. volume and shake again. Add 2 ml. Nessler
reagent, make up to 50 ml. volume and shake.
After 10 minutes read the transmittance at 425 mu wavelength on a
Spectronic 20.
Standards:
Transfer 10 ml. of 0.0, 1.0, 2.0, 4.0 and 6.0 ppm N working stock
solutions into 50 ml. volumetric flasks. This gives standards of 0.0,
0.2, 0.4, 0.8 and 1.2. Use same procedure as for samples to develop
Nessler color after neutralizing with MaOH.
Stock NH4 Solution-100 ppm N
Weigh out 0.1910 grams of reagent grade NtfyCl into a small beaker.
Transfer to 500 ml. volumetric flask, dissolve and make up to volume
with H20. Transfer to suitable glass container. This makes 100 ppm
standard.
Working Stock Solution:
Place approximately 50 ml. of H?0 in each of five 100 ml. volu-
metric flasks. Add 5 ml. of the sulfuric acid selenium oxychloride
solution cautiously, swirl, and allow to cool. Add 0, 1, 2, 4, and 6
ml of the 100 ppm N Standard NH4 solution to the five flasks respective-
ly. Bring the volume up to 100 ml. with H20 and shake. Transfer 10 ml
from each flask to separate 50 ml. volumetrics, neutralize with NaQH
then develop Nessler color as with samples.
Reagents:
9N NaOH - Add 360 grams of U.S.P. grade NaOH per liter H20,
cautiously. Stir and cool.
487
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Gum Arabic Solution - Add 1$ gum arabic by weight to H20 and
shake. 5 grams/ 500 ml.
Sulfuric acid- selenium oxychloride solution - Add 1.5 ml. of
selenium- oxychloride solution per liter of cone. f^SCfy, shake.
Nessler Reagent - Dissolve 300 gm of KOH in 400 ml. distilled F^O and
allow to cool. Dissolve 60 gm HgCl2 in 600 ml. distilled H20 (Apply
heat until dissolved). Dissolve 123.5 gm KL in 500 ml. distilled
in a 2000 ml. volumetric flask. Add the Hg Cl£ solution to the Kl
solution until red precipitate begins to form; then add Hg Q£ drop-
wise until red precipitate does not dissolve by swirling. Add 1.5 gm
of Kl to the solution and the red precipitate should redissolve; shake
well. Add the KQH solution, shake well, cool, make up to volume.
Transfer to a brown bottle and keep in cool dark place. Centrifuge
sub-aliquots if the reagent is not clear.
Ammonium Only
Procedure:
Transfer an aliquot of the sample (5 ml. <10 ppm; 1 ml. 10-60
ppm) into a 50 ml. volumetric flask. Add 0.6 ml. of 9N. NAQH. Add
2 ml. of gum arabic solution. Add water to make volume 35 to 40 ml.
and shake. Add 2 ml. of Nessler reagent and add water to bring up to
50 ml. volume. Shake samples and read transmittance at 425 mu setting
on Spectronic 20 after 10 minutes.
ABS (alkyl benzene sulfonate) - MBAS (methylene blue active substance)
Transfer a 100 ml sample to a 250 ml separatory funnel. If less
than 100 ml of sample is used make up to 100 ml with 1^0. Add 1 ml of
4NH2S04, mix by swirling. Add 10 ml of chloroform and 25 ml of methyl-
ene blue solution. Shake for 30 seconds. Allow chloroform and water
phases to separate. Excessive agitation may cause emulsion trouble.
Drain off chloroform into a second separatory funnel. Repeat
extraction two more times. If blue color in water phase becomes faint
add 25 ml more of methylene blue solution.
To the chloroform in the second separatory funnel add 50 ml of
wash solution. Shake 30 seconds. Allow chloroform to separate out
and draw off through cotton plug in small funnel into a 100 ml volu-
metric flask. Extract wash solution twice more with 10 ml portions of
chloroform. Rinse stem of separatory funnel and cotton plug in funnel
with about 5 ml of chloroform. Dilute to 100 ml mark with chloroform,
and mix well.
488
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Make up 100 ml standards from 0-1.3 ppm, treat same as unknowns.
Measure absorbance at 652 mu on Spectronic 20.
*
ABS Reagents
Standard alkyl benzene sulphonate (ABS) solution (1,000 ppm)
2.0534 gm (Association of American Soap and Glycerine Producers,
New York ) ABS dissolved in 1,000 ml.
Four Normal Sulfuric Acid
Pour 56 ml of cone. H2S04 into 500 of H20 in a liter Pyrex flask,
mix, cool.
Chloroform - use ACS Reagent grade.
Methylene blue reagent
Dissolve 0.1 gm methylene blue in 100 ml of distilled water.
Transfer 30 ml of this solution to a 1-liter flask. Add 500 ml of
distilled water, 6.8 ml of cone. f^SO* and 50 gm of monosodium di-
hydrogen phosphate monohydrate, Nal^PO^t^O. Shake until solution is
complete. Dilute to 1-liter.
Wash solution
Add 6.8 ml cone. H^SO* to 500 ml. of distilled water in a 1-liter
volumetric flask. Then add 50 gm of Nat^PC^ tifl and shake until solu-
tion is complete. Dilute to the 1-liter mark with J^O.
Nitrate Nitrogen
Turn nitrate ionalyzer on and allow to warm up for about 20 min.
before making readings. Check electrodes to be certain that they are
full of filling solutions. Pour out approximately 25 ml of water
sample into a 50 ml beaker. Standardize ionalyzer with 10 ppm and
100 ppm N-NOs standards. Temperature must be set for both standards
and samples. Standards and samples should be read while being stirred
with magnetic stirrer. Instrument should be rechecked with standards
after every 20 samples.
Spectrographic Analysis for K, Ca, Mg, Ma, B and Na
Transfer 100 ml of composite sample to 125 ml evaporating dish
unless the composite sample contains less than 100 ml and then transfer
50 ml of sample. Evaporate sample in an oven set at 105°c. Samples
are then ready to be taken up in lithium-HCl buffer and run on arc
489
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spectrograph. The samples are analyzed for K, Ca, Mg, Mn, B, Na.
Code sheets accompany samples when they are transferred to the spec.
lab.
Orthophosphate Phosphorus
Transfer an aliquot of water containing 0 to 40 ug of phosphorus
to a 150 ml beaker and add distilled H20 to make volume 50 ml. Make
standards of 0.0, 0.2, 0.4, 0.6, 0.8 ppm in 50 ml total volume. (Add
1, 2, 3, 4 ml of 10 ppm stock P to 49, 48, 47, 46 ml of distilled H^O
respectively plus the 2 beakers containing 50 ml distilled H^O). Add
2 ml of sulfomolybdic acid to each standard and each sample and stir
well. Add 0.25 ml of stannous chloride to each standard and sample
except for one of the 0.0 standards, which is used to set 100% trans-
mittance on the Spectronic 20, and stir immediately. The samples
should be read between 6 and 12 minutes after developing with stannous
chloride. Determine transmittance of samples at 690 mu on Spectronic
20.
Sulfomolybdic Acid Solution - Add 310 ml of concentrated
cautiously to 400 ml of distilled H20 in a 1000 ml beaker. Stir arid
allow to cool. To 180 ml of distilled f^O in another beaker ad4 25gm
of ammonium molybdate and stir. After acid has cooled, add molybdate
solution, stir and allow to cool. Transfer to an acid bottle, make
up to 1000 ml. mark, shake, and store in a dark place.
Stannous Chloride Solution - Weigh out 1.25gm of stannous chloride
L7-2H20) in a 30 ml beaker and dissolve in 5 ml of concentrated HC1.
If solution is not clear, heat gently over a flame. Transfer solution
to a 50 ml. volumetric flash, make up to volume, and shake. Store in
dark and make up fresh every week.
Standard Phosphorus Solution: 500 ppm P
Dissolve 2.1950gm of dried KH2PC>4 in about 400 ml of water in a
1000 ml volumetric. Add 5 ml of cone I^SC^ to help preserve the standard.
Dilute to 1000 ml, place in storage bottle, and keep refrigerated.
Phosphorus working standard: Transfer 10 ml of 500 ppm P to a
500 ml volumetric, make up to volume, and shake.
Pour out water sample into 1 oz paper cup (about 3/4 full). The
pH meter is set with pH^i and pHy buffer solutions. Temperature of the
water samples is checked and the meter is set. The samples are then
read and recorded.
490
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Chloride
Transfer 10ml of water sample into a 30ml beaker. Transfer 10ml
distilled ^0 into 30ml beaker for blank at beginning of run and after
every 30 samples. Transfer 20 ml lOOppm chloride standard solution
into 30ml beaker to be run with each blank. Add 10ml of buffer solu-
tion to samples and blanks (buffer is already included in standard).
Add 1ml of gel reagent to all blanks, standards, and samples. High
titration rate should be used for titrating water samples. If silver
electrode is cut to renew, an extra standard should be run to condition
the new silver wire. If microammeter does not return to 0, all elec-
trodes should be thoroughly cleaned and rinsed. Titrator should warm
up 20 min. before titration is begun.
Buffer solution - Add 400 ml distilled H20 to a 1000ml volumetric
flask. Add 200 ml of glacial acetic acid and 12.8 mis of cone nitric
acid; make up to volume and shake.
Gel reagent - Dissolve 0.62gm of gel reagent into each 100ml of
distilled ^0. Heat if necessary. Keep refrigerated.
Standard - transfer Smls of 10,000ppm Cl stock standard to a
1000ml volumetric flask. Add 100ml acetic acid and 6.4ml (concentrated)
nitric acid. Make up to volume and shake.
Stock Solution of Chloride: Weigh out 8.2413 gm of reagent grade
NaCl into a 50ml beaker. Dissolve in distilled ^0 and transfer to a
500ml volumetric flask. Make up to volume, shake, and transfer to a
storage bottle.
SOIL SAMPLES
Exchangeable Cations
Weigh out 5 gm. of dry, sieved soil into a 50 ml. centrifuge tube.
Add 33 ml IN MfyQAc, shake in a mechanical shaker for 5 min. and centri-
fuge for 5 min. at 2000 rpm. Decant supernatant through a Whatman No. 2,
12.5cm filter paper into a 125 ml. porcelain evaporating dish. Repeat
extraction with two additional 33 ml portions of MfyOAc. Soil must be
resuspended in extraction solution before shaking in mechanical shaker.
Evaporate total extract to dryness in oven set at 105Oc. Have residue
taken up in spectrograph buffer and Ca, Mg, K, Na, Mh, B determined on
the spectrograph.
Ammonium Acetate solution: Add 77.08 gm of MtyQA- - per liter of
solution. The solution is then adjusted to pH 7.0 by adding acetic
acid or ammonium hydroxide.
491
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Exchangeable Hydrogen
A 10 gm soil sample is weighed out into a 125 ml erlenmeyer flask.
Add 25 ml of the Ba d.2 buffer solution and shake for 1/2 hrs. The
suspension is then filtered through a Buchner funnel fitted with
Whatman No. 42, 55 mm paper. The soil is completely transferred with
25 ml more of the buffer solution. The soil in the funnel is then
further leached with 100 ml of BaCl2 replacement solution.
The combined filtrates are titrated with standard 0.1N HC1 to an
end point with bromcresol green-methyl red indicator, the color being
standardized against a blank titration of similar volumes of the 2
extraction solutions.
0.5NBaCl2 - buffer solution - add 62.5 g. of BaCl2 2^0 and 25 ml of
triethnolamine per liter of solution.
0.5N Bad? - replacer solution - Add 62.5 g. BaCl^F^O and 2.5 ml. of
buffer solution per liter of replacer solution.
Bromcresol green - 0.5% in ethanol
Msthyl red - 0.2% in ethanol
Soil Organic Matter
Transfer a weighed quantity of soil (ground to pass a 0.5 nta sieve)
containing 10 to 25 mg of organic carbon. (Use O.Sg for 1st foot,
2 gm for 2nd foot, and 3 gm for 3rd through 5th foot on waste water
project soils) into a 250 ml erlenmeyer flask. Add 10 ml of N potassium
dichromate and then 20 ml of concentrated sulfuric acid, directing the
stream into the solution. Immediately swirl vigorously for 1 min. and
let the flask stand on a sheet of asbestos for about 30 minutes. Then
add 100 ml of water, 10 ml of phosphoric acid, swirl and allow to cool.
Add 4 drops of ferroin indicator. (1,10-phenanthroline, ferrous
sulfate complex)
Proceed with the titration as follows: Add the ferrous sulfate
solution until the solution begins to change from a reddish-brown to
a grayish color then add the ferrous sulfate dropwise until a permanent
gray color exists . If more than 8 ml of the available 10 ml of potas-
sium dichromate is reduced, the determination should be repeated with
less soil. The ferrous sulfate is standardized against a blank of 10ml
of NK2Cr20y plus all other reagents.
IN Potassium dichromate solution - Dissolve 49.04 gm of reagent
grade I^C^Oy in water and dilute to 1 liter.
492
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o.5N Ferrous ammonium sulfate solution - Dissolve 196.08 gm of
Fe(NH4)2-(SC>4)2 6H20 plus 40 ml. o£ concentrated H2S02 per liter of
cr\1 ii-f"-i/"vr\
solution.
Soil pH
The soil pH is determined on a 1:1 soil to water mixture. Ten
grams of air dry, sieved (passing 10 mesh) soil is measured into a 1
oz paper cup. Ten milliliters of distilled H20 is then added to the
soil and stirred. The soil is allowed to stand for 15 min. and then
stirred again. After standing another 15 min. the soil is stirred
and immediately the pH is read on any suitable pH meter.
Soil Chloride
A 2gm sample of dry, sieved soil is weighed out into a 125 ml
erlenmeyer flask. Twenty.ml of 0.05N NH4N03 is added to the flask
and shaken on a mechanical shaker for 5 minutes. The suspension is
then filtered through Whatman No. 2, 12.5cm filter paper into a 50
ml beaker. A 10ml aliquot of the filtrate is then transferred to a
30 ml beaker; 10 ml of buffer solution and 1ml of gel reagent are
added. The samples are then titrated on the Aminco-Cotlove Chloride
titrator. Run standard and blank before samples are started and after
every 30 samples. Standard: Transfer 2.5 ml of 10,000 ppm stock
chloride solution into a 1000ml volumetric flask. Make up to volume
with 0.05N MfyNC^ and shake. Use 10 ml of this solution for standard,
add 10ml buffer solution, and 1ml gel reagent.
Buffer solution: Add 400 ml dist H20 to a 1000ml volumetric flask.
Add 200 mis acetic acid and 12.8 mis nitric acid; make up to volume
with H20 and shake.
Gel reagent: Dissolve 0.62g.gel reagent in 100 ml distilled H20.
Keep refrigerated.
Stock Chloride Solution: Weigh out 8.2413gm of regent grade NaCl
into a 50 ml beaker. Dissolve and transfer to a 500ml volumetric
flask. Make up to volume, shake, and transfer to a storage bottle.
Extractable Soil Phosphorus
A 2.85 gm sample of crushed, sieved (2mm) soil is weighed out
into a 50 ml bottle or test tube. 20 ml of extracting solution
(O.OSN-NffyF in 0.025N-HC1) is added and the bottle is stoppered and
shaken for 1 minute. The suspension is immediately filtered on a
moist Whatman No. 42 filter paper in a funnel. 2 ml of the clear
493
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filtrate is transferred to a colormeter tube, then 5 ml of water is
added and mixed. The 2 ml of molybdate is added and mixed followed by
addition of 1 ml of freshly diluted stannous chloride with immediate
mixing. After 5-6 minutes and before 15-20 minutes the blue color is
read at 690 mu on a Spectronic 20.
The ammonium molybdate reagent was made by dissolving 15 grains of
ammonium molybdate in 300 ml of distilled water warmed to 50°C. After
cooling add 350 ml of 10.0N-HC1 slowly with rapid stirring. The solu-
tion is then diluted to 1000 ml and stored in an amber, glass stoppered
bottle.
The stannous chloride stock solution is made by dissolving 10 grams
of stannous chloride in 25 ml of concentrated HC1. It is kept in a
dark, tightly stoppered bottle. For each day's run a freshly diluted
solution was prepared by adding 1 ml of the stock solution to 330 ml
of freshly boiled, cooled, distilled water.
PLANT SAMPLES
Total Nitrogen in Plant Material
Weigh out and transfer a 0.25gm plant sample into a 125ml Pyrex
erlenmeyer flask. Add 5ml of salicylic-sulfuric acid mixture and allow
to stand 30 minutes, swirling occasionally to insure complete contact
of acid and plant material. Add 4 drops of sodium thiosulfate solution,
swirl, add 5ml of selenium oxychloride-sulfuric acid solution. Mix
thoroughly. Heat gradually to boiling on a hot plate under a hood and
digest until clear. If the solution is not colorless, add 2-3 drops
of 10% perchloric acid and swirl. Heat again slowly until solution
is colorless but do not boil.
Transfer solution to a 100ml volumetric flask, fill to volume and
"shake. Transfer a 1ml (for corn-0.5ml for Reed Canary Grass) aliquot
of the solution to a 50ml volumetric flask. Neutralize with NaOH
(approximately 0.8ml of 9N NaOH). Fill flask to 35-40ml with distilled
H20. Add 2 ml of gum arabic; swirl. Add 2ml of Nessler reagent, make
up to volume and shake. Read samples and standards-at 425 mu wave
length on Spectronic 20 or similar photometer.
Calculation of Total Nitrogen
1ml = Dilution Factor: 1:20,000 (Corn)
0.5ml = Dilution Factor: 1:40,000 (Reed Canary Grass)
thus: ppmN x 2.0 = TN in % N (Corn)
ppmN x4.0 = TNin%N (Reed Canary Grass)
494
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Reagents:
Salicylic-sulfuric acid solution - Add 32gm of salicylic acid
per liter concentrated H2SC>4.
Sodium thiosulfate solution - 70.45gm NaoSoO?. 5H70 per 100ml
of distilled H20.
Selenium oxychloride-sulfuric acid - 1.5ml of selenium oxychloride
per liter concentrated
Plant Ashing Procedure
Samples are ashed in vitrex crucibles. Vitrex crucibles must be
washed in alkanox solution, rinsed, dipped in 0.1 N HC1 and rinsed
thoroughly with distilled H20. The crucibles must then be dried, with
care being taken to avoid dust settling into the crucibles. One gm.
of the plant material, to the nearest .0001 of a gm., is then weighed
into each crucible which is placed in a steel and asbestos tray. The
grays are placed in the muffle furnace, the exhaust hood is started,
and the muffle furnace heated to 485°C. Samples are ashed for 8 hrs.
and then cooled gradually to room temperature.
After cooling, the ashed samples are removed from the muffle
furnace and transferred to plastic bottles with assistance of silver
plated funnel and camel hair brush. Caution should be exercised to
avoid breezes. Samples are then ready for spec analysis by the method
of Baker, et al (81).
Chloride Determination in Plant Material
Weigh O.SOgm of plant material into a 125ml erlenmeyer flask.
Add 20ml of 0.05 N NH^N03. Digest on steam bath for one hour, filter
while hot through a filter paper (Whatman No. 2) into a 100 ml volu-
metric flask. Wash filter and residue with three additional 20ml
portions of hot 0.05N NH^MC^. Cool filtrate to room temperature make
up to volume with distilled water, shake to mix. Transfer a 10ml
aliquot to Aminco-Cotlove titrator beakers, add 10ml of nitric-acetic
acid buffer and 1 ml of gelatin and proceed with titration.
Select standard chloride concentration and switch position on
titrator to keep titration time less than 100 seconds. Use 0.05 N
in making up standards and blanks.
Standard - Add 5 ml of 10,000ppm Cl Stock solution to 400ml of
0.05N MfyNC^ in a 500 ml volumetric flask. Make up to volume and shake.
Use 10ml standard + 10ml of buffer solution for each standard.
Blank - Add 100ml dist H20 to 400ml 0.05N NH4N03= Stir. Use 10ml
of this solution + 10ml buffer solution for each blank.
495
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SELECTED WATER
RESOURCES ABSTRACTS
INPUT TRANSACTION FORM
4. Title
Renovation of Secondary Effluent for Reuse as a
Water Resource
7. .^•rtAorrsj..KM^os> L. T., Sopper, V. E., Myers, E. A.,
Parizek, R. R., and Nesbitt, J. B.
9. Organization
The Pennsylvania State University, University Park, Pa. 16802
Depts. of Agronomy, Forest Science, Ag. Eng., Geol. Science,
Civil Eng.
/5, Supplementary Notes
Environmental Protection Agency, report number
EPA-660/2-74-016, February 1974.
10. Project No.
11. Contract/Grant No.
16. Abstract Sprinkler application of chlorinated secondary sewage effluent at levels of
1 or 2 in/wk during the growing season or year-round increased crop yields and forest
tree growth except for red pine at the 2 in/wk rate. Harvested crops removed large
amounts of nitrogen and phosphorus, the two key eutrophication nutrients. N and P con-
tent of forest foliage was increased but the nutrients were recycled through the litter.
N03-N in suction lysimeter samples at 4 feet were less than the U.S.P.H.S. limit of 10
rag NOs-Wl. except on the growing season-2 in/wk red pine on Hublersburg silt loam and
year-round, 2 in/wk hardwood on itorrison sandy loam, where the,values were 2 to 4 times
the U.S.P.H.S. limit. P cone, in the'same samples was no greater than in untreated con-
trol areas and had decreased 98 to 99%. Only one deep monitoring well showed higher NDJ
and d~ cone, definitely ascribable to the effluent irrigation but still met U.S.P.H.S.
drinking water standards. Recharge within one 43.5 acre site was estimated at .65 mil-
lion gallons per year and resulted in lower pumping costs in two nearby University water
supply wells. , Annual costs of a sprinkler irrigation system to recycle sewage effluent
through the land as a living filter were estimated to range from $13/EDU for BCD to
$8/EDU for 10MSD. Data are also reported on hydrologic studies, boron studies, aeration
studies, phosphorus adsorption studies and soil chemical changes.
na. Descriptors *Lj.ving filter, *Sewage effluent, *Land disposal, *Wastewater reuse,
*Phosphorus removal, *Water pollution, Nitrates, Boron, Groundwater recharge. Sprinkler
irrigation, Crop production, Tree growth, Oxygen diffusion, Exchangeable cations, Bray
phosphorus, Nutrient removal efficiency, Manitoring, Suction lysimeters, Trench lysi-
meters, Piezometers, Runoff, Deep wells, Annual costs.
nb. identifiers Com (grain), Oofti (silage), Reed canarygrass, White spruce, Red pine,
Hardwoods, *Hublersburg clay loam, *Morrison sandy loam, *State College, Pa.
ire. COWRR Field & Group OSDj, OSE, OSF, 05B, 04B, 03C, 02G.
18. Availability
Abstractor L. T. Kardos
Send To:
WATER RESOURCES SCIENTIFIC INFORMATION CENTER
U.S. DEPARTMENT OF THE INTERIOR
WASHINGTON. D C. ZO24O
institution The Pennsylvania State University
WRSIC 102 (REV. JUNE 1971)
* O. S. GOVERNMENT PRINTING OFFICE : 1974 720-064/502
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