United States
Environmental Protection
Agency
Municipal Environmental Research EPA-600/2-80-002
Laboratory ' ' , ' March 1980
Cincinnati OH 45268
Research and Development
Effects of Sludge
Irrigation on Three
Pacific Northwest
Forest Soils
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RESEARCH REPORTING SERIES
Research reports of the Office of Research and Development, U.S. Environmental
Protection Agency, have been grouped into nine series. These nine broad cate-
gories were established to facilitate further development and application of en-
vironmental technology. Elimination of traditional grouping was consciously
planned to foster technology transfer and a maximum interface in related fields.
The nine series are:
1. Environmental Health Effects Research
2. Environmental Protection Technology
3. Ecological Research
4. Environmental Monitoring
5. Socioeconomic Environmental Studies
6. Scientific and Technical Assessment Reports (STAR)
7. Interagency Energy-Environment Research and Development
8. "Special" Reports
9. Miscellaneous Reports
This report has been assigned to the ENVIRONMENTAL PROTECTION TECH-
NOLOGY series. This series describes research performed to develop and dem-
onstrate instrumentation, equipment, and methodology to repair or prevent en-
vironmental 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.
This document is available to the public through the National Technical Informa-
tion Service, Springfield, Virginia1 22161.
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EPA-600/2-80-002
March 1980
EFFECTS OF SLUDGE IRRIGATION ON
THREE PACIFIC NORTHWEST FOREST SOILS
by
David D. Wooldridge
and
John D. Stednick
College of Forest Resources
University of Washington
Seattle, Washington 98195
Grant No. R-802172
Project Officer
Gerald Stern
Wastewater Research Division
Municipal Environmental Research Laboratory
Cincinnati, Ohio 45268
This study was conducted in cooperation with
Municipality of Metropolitan Seattle
Seattle, Washington 98104
MUNICIPAL ENVIRONMENTAL RESEARCH LABORATORY
OFFICE OF RESEARCH AND DEVELOPMENT
U.S. ENVIRONMENTAL PROTECTION AGENCY
CINCINNATI, OHIO 45268
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DISCLAIMER
This report has been reviewed by the Municipal Environmental Research
Laboratory, U. S. Environmental Protection Agency, and approved for publi-
cation. Approval does not signify that the contents necessarily reflect the
views and policies of the U. S. Environmental Protection Agency, nor does
mention of trade names or commercial products constitute endorsement or
recommendation for use.
tt.
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FOREWORD
The Environmental Protection Agency was created because of increasing
public and government concern about the dangers of pollution to the health
and welfare of the American people. Noxious air, foul water, and spoiled
land are tragic,testimony to the deterioration of our natural environment.
The complexity of that environment and the interplay between its components
require a concentrated and integrated attack on the problem.
m Research and development is that necessary first step in problem solu-
tion and it involves defining the problem, measuring its impact, and searching
for solutions. The Municipal Environmental Research Laboratory develops new
and improved technology and systems for the prevention, treatment, and *
management of waste water and solid and hazardous waste pollutant discharges
from municipal and community sources, for the preservation and treatment of
public and aesthetic effects of pollution. This publication is one of the
products of that research; a most vital communications link between the
researcher and the user community.
m Major metropolitan areas are encountering increasingly complex problems
with disposal of wastes. This report addresses one phase of the problem--
disposal of municipal-industrial sewage sludge. Cities in forested regions
can dispose of sludge in forests with economic benefits and no significant
environmental consequences.
Francis T. Mayo, Director
Municipal Environmental Research
Laboratory
m
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ABSTRACT
Forested regions of the United States offer an alternative for disposal
of liquid wastes with the potential benefits to Society of economical waste
disposal and accelerated forest growth. Digested liquid municipal sludges
contain bio-degradable nutrients and sufficient water to enhance forest
growth. Study was initiated in May 1974 of efficient methods of liquid sludge
and chemical properties of forest soils and chemistry of soil water. A
sprinkler irrigation system was developed for uniform applications of sewage
sludge to forest plots.
The renovation capacity of the forest soil for most suspended and dis-
solved constituents in sewage sludge is very good (95 to 99+/*). Nitrogen is
the exception as nitrification rates increased with increased rates of sludge
applications, resulting in significant leaching of N03-N and concomitant
'cation losses. Phosphorus in all forms was never found in significant amounts
in soil solutions of tested soils.
Sludqe applications generally increased the growth rate of the forest
stand. Water applied after sludge irrigation may further enhance tree growth
over sludge only applications. Heavy metals were either absorbed in the
aluminum oxide lysimeter plates or tied up in the soil P™file. Human
pathogens of the bacteria and virus types were not isolated from the limited
number of soil and soil solutions analyzed.
This report was submitted in fulfillment of grant R-802172 by the
University of Washington under the sponsorship of the U. S. Environmental
Protection Agency and the Municipality of Metropolitan Seattle, Washington
cooperatively with the Weyerhaeuser Company. This report covers a period of
May 1, 1974 to April 30, 1978, and work was completed as of September 29,
1978.
iv
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CONTENTS
Foreword .... .......
Abstract ............ . ................. ".J
Figures ................ !.'!.'.'.'.',' ....... viii
Tables .................... . ! . . ...... x
Abbreviations and Symbols .......... ............ xii
Acknowledgements ............ ............ xiv
1. Introduction ...... . ............. -i
Research Objectives ............ '. .' . . . . . i
2. The Study Area ..... . .............. 3
Climate ............ ...... ....... 3
The Everett Soil Series ........... ...... 4
The Mashel Soil Series ............ ...... 6
The Wilkeson Soil Series ...... ........... 7
3. Methods of Plot Layout, Soil Sample and Analyses ... in
Plots on the Everett Soil Series . ........... ' -\Q
Soil Solution Monitoring ......... . . . . . 12
Sampling for Ground Water Nutrients ........... 12
4. Sludge Treatment to Plots . . . ......... 15
Plots on Mashel and Wilkeson Soils ........ '. . '. '. 15
5. Analytical Analyses of Soils, Soil Solutions and Ground Water 17
Soil Properties ........... . ..... * -jy
Soil Solution and Ground Water Analyses' . . ....... 18
Virus Determination .... ..... .....!'**' 19
Total and Fecal Col i form Determinations' .' .'.'!.'!.'.'! 19
6. Total Organic Carbon Components ................ 20
Total Organic Carbon Measurements ............ 20
7. Biological Decomposition ......... ......... 22
Decomposition Analyses ........ ........... 22
8. Evaluation of Tree Growth ,..,....„ .......... 24
9. Liquid Waste Processing and Sludge Properties ......... 26
Chemical Composition of Sludge .... ..... •!.'.'!.* 26
10. Study of Sludge Application Methods .... 29
Sprinkler Modifications .......... '.'.'.'.'.'.'. 30
11. Summary of Tests of Sludge Application Methods .... 35
Over-the-Canopy Application ............. ' 35
Trickle Irrigation Application ......... ' 35
Under- the- Canopy Irrigation ......... ' 35
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CONTENTS (Continued)
12. Initial Sludge Applications 39
Sludge Applications and Constituents 39
13. The Irrigation System and Sludge Application Rates 41
First Year Applications 41
Second Year Applications • • • 41
14. Results of Sludge Applications on Soils and Soil Water .... 43
Renovation of Solids 43
15. Everett Soils, Soil Solution Nutrients 46
16. Properties of Everett .Soils 54
Everett Soil Chemistry, First and Second Years 56
Everett Soils, Exchangeable Chemistry and Base Saturation,
Second Year 59
Everett Soil Chemistry, Third Year 61
Everett Soils, Exchangeable Chemistry and Base
Saturation, Third Year 63
Everett Soils, Reduced Sludge Applications 65
Everett Soil Chemistry, Reduced Sludge 65
Everett Soils, Exchangeable Chemistry and Base
Saturation, Reduced Rates ..... 68
17. Everett Soil Solution Nutrients, Water and Control Plots .... 70
18. Everett Soils—Soil Solution Nutrient Concentrations ...... 72
Total Nitrogen • • • 72
Base Nutrients /4
Everett Soils, Soil Solution Conductivity, pH and
Alkalinity 74
19. Everett Soils, Ground Water Nutrients 77
20. Mashel Soils, Soil Solution Nutrients . 79
Nutrient Renovation for the Mashel Soil Series ...... /9
21. Mashel Soil Properties • 82
Soil PH • f
Soil Organic Matter °£
Total Nitrogen ....... 82
Cation Exchange Capacity tf^
Carbon-Nitrogen Ratio •; • • • %„
Mashel Soils, Exchangeable Cations and Base Saturation . . 84
22. Wilkeson Soils, Soil Solution Nutrients 86
Wilkeson Soils, Soil Properties ...... 86
Wilkeson Soils, Exchangeable Cations and Base Saturation . 89
/
23. Mashel and Wilkeson Soils, Soil Solution Nutrient
Concentration » . . . 91
24. Everett Soil, Total Organic Carbon .... 93
Total Organic Carbon Leaching • • y
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CONTENTS (Continued)
Identification of Specific Organics . „ 96
25. Everett Soil, Biological Decomposition 105
Soda Solubility 105
Weight Loss Decomposition 108
26. Everett Soils, Virus and Bacteria ....... 112
27. Everett Soils, Heavy Metals - . . 113
28. Sludge Applications and Forest Growth 114
Sludge Application and Forest Growth, Paried Trees .... 117
Diameter Growth Rate, Paired Trees . 117
Basal Area Growth Rate, Paired Trees ..... 121
Volume Analysis 121
Water Only Irrigation, Growth, Paired Trees 121
'• Sludge vs. Sludge Plus Water, Growth, Paired Trees .... 121
29. Discussion of Sludge Applications to Forest Soils 126
Sludge Application Methods . . 126
Rates of Sludge Application ..... 127
Renovation of Nutrients 128
Renovation of Base Nutrients ..... 128
Renovation of Phosphorus ..... 129
Renovation of Nitrogen 129
Evaluation of Total Organic Carbon ............ 131
Evaluation of Biological Decomposition 131
Sludge Applications and Forest Growth 132
30. Summary of Results of Sludge Applications „ 133
Literature Ctted 135
Appendices ............. 138
vn
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FIGURES
Number
1 The Everett soil series is an immature, slightly podzolic
soil developed on loose, poorly sorted glacial outwash ....... 5
2 Plots on the Wilkeson soil were in an old growth western
hemlock stand with larger older trees and an understory of
young hemlock. The plywood box contains the sample collection
bottles for the lysimeter plates ................. • 9
3 The Everett soil supports a 36-year old Douglas-fir stand
with an average of 1580 trees per ha. Standing dead trees and
cull hardwoods were removed from the plot (pile in lower
righthand corner) ................... ....... 11
4 The arrangement of plots and treatments is shown for the study
area on the Everett soils. Plot numbers are in parentheses
while treatments indicate the mt/ha/yr. Locations of wells
are shown with an XI, etc ....... .............. 13
5 Sludge was transported from Metro's West Point Plant to Pack
Forest in 19,000-liter quantities (5,000-gal . ). Usually
two trips were made each day sludge was applied ...... .... 30
6 A ramp was constructed so the tanker trucks could discharge
sludge by gravity flow to the storage pond ........... . . 31
7 Adjacent to the storage pond, a small structure housed the
combination Maz-o-rator and Moyno pump. Piping to the right
is the suction line from the storage pond with the supply
lines to plots underground. ,.. ................... 32
8 The Rainbird 65D TNT sprinkler had the lower deflector arm
removed and was teflon coated, following removal of rough
projections in the brass casting. . . ............ .... 34
9 Heavy rates of sludge application caused impeded infiltration
resulting in ponding of sludge in depressions. This example
from the trickle irrigation plot in an area of concentrated
sludge applications ................... ...... 36
10 Sprinklers were located on 5-ft. risers at each corner
on the square plots ................... „ .... 38
11 Average TOC values versus depth for water, control, and
sludge treatments .................... ...... 94
12 Average TOC versus soil depth for the sludge followed
by water sites ...................... ..... 95
vi i i
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FIGURES (Continued)
Number
13 TOC versus date of sample collection for the 300 plot
from the four soil depths 97
. 14 L layer and C horizon soil solutions from sludge control
plots compared by gel filtration chromatography 98
15 Gel filtration chromatograms of soil solution samples from L
and C layers of 10 .series plots, C horizon of 300 plot
and well water. 99
16 Gas chromatogram of ether extract of soil from 300 and
control plot A horizon using a DEGS column 101
17 Gas chromatogram of ether extract of soil from 300,and
control plot B horizon using a DEGS column. . . . 102
18 Gas chromatogram of ether extract of 100 B horizon using
a DEXSIL 300 column 103
19 Gas chromatogram of ether extract of the control plot B
horizon using a DEXSIL 300 column 104
20 Changes in 1% NaOH solubility of wood blocks on top of the
litter over time by sludge treatments 106
Changes in net weight of wood blocks on top of the litter
over time by sludge treatments HO
Individual tree'diameter pai following 3 years of irrigation
as a function of pretreatment diameter pai per tree
(paired trees). . , ]18
23 Individual tree basal area pai following 3 years of
irrigation as a function of pretreatment basal area
per tree (paired trees) 122
24 Adjusted mean diameter pai following 3 years of irrigation
as a function of weekly irrigation rates 124
21
22
IX
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TABLES
Number
Page
1 Maximum, minimum and average composition of sewage
sludge applied to plots. 27
2 Tons of sludge applied by plots and soils and year
in depth and total weights • 45
3 First year nutrient loading and flux (kg/ha) through the
Everett soil and percent renovation 47
4 Second year nutrient loading and flux (kg/ha) through the
Everett soil and percent cumulative renovation .......... 49
5 Third year nutrient loading and flux (kg/ha) through the
Everett soil and percent cumulative renovation ..... 51
6 Total nutrients applied (kg/ha), flux and percent total
renovation through Everett soil. . . 52
7 Total nutrient balance for pre- and post sludge applications
and total percent flux on the Everett soil 55
8 Soil chemical properties following sludge applications on
the Everett soil series and 95% confidence interval,
second year 57
9 Exchangeable cations and percent base saturation by
horizons of the Everett soil, second year 60
10 Soil chemical properties following sludge applications on
the Everett soil series and 95% confidence interval,
third year 62
11 Exchangeable cations and percent base saturation by
horizons of the Everett soil, third year 64
12 Total nutrient loading and flux (kg/ha) through the
Everett soil • 66
13 Average soil chemical properties of Everett (new plots)
soils with reduced rates of sludge application ...... 67
14 Exchangeable cations and percent base saturation by horizons
for pre- and post sludge applications for the Everett
soil (reduced rates) 69
15 Nutrients applied in water and flux (kg/ha) from control
and water only plot 71
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TABLES (Continued)
Number Page
16 Minimum-maximum concentrations of nutrients in the soil
solution at 2.1 m (7 ft.), Everett soils . 73
17 Conductivity, pH, and alkaninity of the soil solution and
ground water for Everett plots 75
18 Dissolved chemistry of ground water, Everett soils 78
19 Nutrient loading and flux (kg/ha) through the Mashel soil
and percent renovation (applied nutrients in mt/ha and
flux of nutrients in kg/ha) 80
20 Soil chemical properties following sludge applications
on the Mashel soil series 83
21 Exchangeable cations and percent base saturation by
horizons for pre- and post sludge applications for the
Mashel soil 85
22 Nutrient loading and flux (kg/ha) through the Wilkeson
soil and percent renovation 87
23 Soil chemical properties following sludge applications on
the Wilkeson soil series and 95% confidence interval. 88
24 Exchangeable cations and percent base saturation by
horizons of the Wilkeson soil . . . . 90
25 Range in nutrient concentrations of the soil solution by
plots for the Mashel and WiVkeson soils 92
26 Decomposition over time assessed by soda solubility extractions
(percentage of dry weight) of wood blocks by various
depths and treatments , 107
27 Decomposition over time assessed by weight loss (percent
of the dry weight) of wood blocks by depths and treatments. ... 109
28 Average stand conditions before and after sewage sludge
irrigation by plot and treatment 115
29 Average gross periodic annual increment for pretreatment,
2 and 3 years after irrigation by plot and treatment 116
30 A summary of average periodic annual increment for paired
trees, before, 2 and 3 years after sludge applications by
treatment 119
31 Comparisons of sludge treatments, water only and the control
using individual paired trees 120
32 Comparison of tree growth slopes between sludge and
sludge plus water treatments 123
XI
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ABBREVIATIONS AND SYMBOLS
ABBREVIATIONS
ac.
BA
cm
DBH
ev
ft.
ftVac
ftVac
9
gal.
g/cm3
ha
hp
in.
kg ,
kg/cm2
km
1
Ibs/ac.
m
meq
Metro
mg
mi.
min.
ml
mm
MPN
mVha
mVha
mt/ha
mt/ha/yr
O.D.
pai
ppm
psi
rpm
sq. ft.
sq. m
acre
basal area
centimeter '..,*.
diameter breast height (the 4.5 ft. or 1.4 m height on
the bole)
electron volts
foot/feet
square feet per acre
cubic feet per acre
gram
gallon
grams per cubic centimeter
hectare
horsepower
inch
kilogram
kilograms per squre centimeter
ki1ometers
liter
pounds per acre
meter
mi Hi-equivalent
• Municipality of Metropolitan Seattle
. milligram
• mile
• minute
- milliliter
• millimeter
- most probable number
• square meters per hectare
- cubic meters per hectare
- metric tons per hectare
- metric tons per hectare per year
- oven dry
- periodic annual increment
- parts per million
- pounds per square inch
- revolutions per minute
- square foot/feet
- square meter
xn
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ABBREVIATIONS AND SYMBOLS (Continued)
vol
yr.
vol ume
year
SYMBOLS
Ca
Cd
Cl
Cn
C02
Cr
K
Mg
Na
NH4+
NHd-N
Ni
N03-N
Pb
PH
P04-P
TOC
Total N
Total P
Zn
-- calcium
— cadmium
— chlorine
-- copper
— carbon dioxide
-- chromium
-- potassium
-- magnesium
— sodium
— ammonium ion
— ammonium nitrogen
— nickel
-- nitrate nitrogen
— lead
-- acidity
phosphate phosphorus
-- total organic carbon
— total Kjeldahl nitrogen
— total phosphorus
— zinc
a
<
U
— alpha
-- less than
— micro
percent
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ACKNOWLEDGEMENTS
The cooperation of the Municipality of Metropolitan Seattle (Metro),
Mr. Ralph Domenowske, project officer, and the Weyerhaeuser Company,
Dr. Ronald L. Heninger, research silviculturalist, Western Forestry Research
Center, Centralia, Washington, is gratefully acknowledged. Drs. Bjorn
Hrutfiord and Charles- Drive of the College of Forest Resources, respectively,
provided the Total Organic Carbon and Biological Decomposition Analyses,
Results and Discussion of findings. The Children's Orthopedic Hospital, as
well as Metro, provided biological analyses and aided in interpretation of
data.
The principal investigator would like to acknowledge personal contri-
bution of Dr. John Stednick to the project as well as other staff personnel,
Kathy McCreary and Bill Wilson, and numerous students who suffered through a
lengthy series of immunization shots for typhoid, cholera, hepatitis, etc.
The contributed secretarial services of my wife, Joyce, in completion of the
final manuscript must also be acknowledged. The research project could not
have been accomplished without their contributions.
Mr. Gerald Stern, project officer, U. S. Environmental Protection Agency,
provided invaluable guidance throughout the three plus years required in the
conduct and reporting of the study. Again, successful completion could not
have been achieved without his help.
xiv
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Section 1
INTRODUCTION
A national objective of improved quality of the Nation's waters has been
implemented through state and federal laws and regulations. These laws and
regulations have far reaching effects on disposal of wastes. Major munici-
palities concentrate both industrial and municipal solid and liquid wastes.
Concentrations of urban population tend to concentrate problems with waste
disposal. Rural and agricultural areas, both domestic and foreign, produce a
host of products utilized in urban centers. Advent of the kitchen sink dis-
posal unit transfers considerable of the solid waste disposal problems to the
liquid waste system, with large quantities of organic wastes processed
through liquid waste digestion rather than solid waste processes.
Burial, burning and disposal in water have become questionable solutions
in waste disposal. Regions of the United States with extensive forest lands
have the opportunity for beneficial use of certain of these liquid wastes in
the forest. Water has an irrigation benefit during summer periods of soil
moisture stress, and utilization, of bio-degradable nutrients by the forest
ecosystem will accelerate forest growth rates.
A research project funded in part by EPA and cooperative with the
Weyerhaeuser Company, the Municipality of Seattle (Metro), and the College of
Forest Resources, University of Washington studied application of liquid
digested wastewater sludge in the forest environment. When applied to the
forest, liquid digested municipal sludge can increase tree growth rates by
adding nutrients and improving soil moisture. The renovation capacity of the
forest soil and utilization of nutrients is dependent upon a series of physi-
cal, chemical and biological interactions in the forest ecosystem.
RESEARCH OBJECTIVES
To accurately interpret the impacts of sludge application on forest
soils, as well as growth rate of trees on the forest plots, a very uniform
liquid sludge application was required so that each area of each plot was
receiving equal quantities of sludge and water.
1. Establish efficient methods of sludge application to forests.
2. Establish the short-term impacts of sludge application on the
forest including effects on physical and chemical properties of the forest
soil and chemistry of soil water.
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3. Establish the rate of sludge application which has maximum benefits
to forest growth with minimum impact on soil water quality and be non-
polluting to surface or ground waters.
4.
rates.
Establish the effects of application of sludge on forest;growth
The above objectives address applied sludge disposal problems, searching
for economic solutions to liquid waste or sludge management. A variety of
experimental designs would answer certain of the questions. These could
include laboratory studies of leaching sludge in soil columns for soil and
water chemistry; however, the complex interactions of weather, soils and
related environmental factors suggested a field study, particularly for devel-
oping an effective method of sludge application in the forest environment and
forest growth responses to applications of sludge.
The following report provides results of three years' study on applica-
tions of municipal-industrial sludge on a series of forest plots on soils
with varying characteristics. By the very nature of the study, it. was
necessary to develop it in phases. The first year concentrated on develop-
ment of the most feasible method of obtaining uniform application of the
sludge to forested research plots.
The requirement for a uniform application of sludge over the experimental
plots required a more complex sludge irrigation system than would be required
for routine disposal of sludge in the forest environment. In the following
sections, the results of the application phase of the study (Objective 1)
will be reported prior to the other results, as this phase developed the
final method of application which was used on plots established in later
phases of the research.
The second year concentrated on determination of the impacts of varying
rates of sludge application. The final phase investigated the impacts of
both rates of sludge application to plots and impacts on three different
forest soil types.
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Section 2
THE STUDY AREA
The research sites are located 110 km (70 mi.) south of Seattle,
Washington near the town of Eatonville and adjacent to and on Pack
Demonstration Forest, College of Forest Resources, University of Washington.
The initial work tested methods of liquid digested sludge application on a
1.6-ha (4-ac.) tract of Weyerhaeuser Company land at lower elevations on the
Everett soil series. Later research assessed weekly rates of sludge applica-
tion on the Everett, Mashel and Wilkeson soils series on Pack Forest. Forest
growth, decomposition and aggregate impacts of three years of sludge applica-
tion on soil and soil water chemistry were studied on the Everett soil series
on Weyerhaeuser Company lands. Research on the Wilkeson and Mashel series
was limited to impacts of rates of sludge application on soil and soil water
chemistry.
CLIMATE
Climate in the vicinity of the study area has in general characteristics
of the maritime climate of the Puget Sound Lowlands. Summers are relatively
warm and dry followed by humid temperate winters with substantial winter
rainfall. Annual precipitation increases markedly with increased altitude,
an average of 35.4cm (10 in.) per year per 305 m (1000 ft.) increase in
elevation, with a marked decline in average annual temperature with increas-
ing altitude. Air masses originate over the Pacific Ocean moderating both
winter and summer temperatures. Precipitation is usually caused by orographic
storms resulting in persistently high moisture content of winter air masses.
Widespread precipitation of moderate to light intensity occurs as air masses
cool and rise over land in winter. Fifty percent (60 cm or 24 in.) of the
average total annual precipitation (120 cm or 48 in.) at Pack Forest falls in
the four months of October through January. Total rainfall for July and
August is usually less than 5% (11.9 cm or 4.7 in.) of the annual and often
drought-like conditions may exist on well drained soils. At lower elevations
(the Everett soil series), snow is common in the winter but seldom persists
for over a few days. At higher elevations (the Wilkeson soil series), snow
is more frequent and persistent.
During the warmest summer months, average maximum monthly temperatures
are 21 to 24 °C (70 to 75 °F), while the coldest winter temperatures average
slightly above freezing.
Annual evaporation from a Class A pan is estimated at 63.5 cm (25 in.)
at nearby Puyallup, Washington 24 km (15 mi.) to the northwest. Monthly
-------
evaporation rates vary from 7.5 to 16.5 cm (3 to 6.5 in.). Based on average
normal temperatures and precipitation, estimates of actual annual evapo-
transpiration range from 38 to 46 cm (15 to 18 in.) in the mountains to 38 to
56 cm (15 to 22 in.) in the lower valleys (Pacific Northwest River Basin
Commission, 1970).
THE EVERETT SOIL SERIES
The Everett soil series is a light colored, podzolic soil developed on
loose gravelly to slightly modified or poorly sorted glacial dutwash. Strati-
fication is usually poor with a wide range in particle sizes of rocky gravelly
components. The research site has a gravelly outwash overburden of 9 to 12 m
(30 to 40 ft.) of gravelly outwash deposits covering a fine textured lacus-
trine strata. The lacustrine strata is almost impermeable to vertically
percolating soil water; thus, most ground water flows laterally along the
interface forming several springs in the vicinity of the research plots.
The soil classified as an Everett type is very coarse textured, immature,
formed from these outwash deposits of the last glaciation. Everett soils are
light colored podzolic soils developed on loose, coarse, gravelly, slightly
modified or poorly sorted glacial outwash materials, stratified in places and
having a wide range of rocks (Figure 1).
The Seventh Approximation (SCS, 1960) groups the Everett series in the
brown podzolic group as a gravelly-loamy sand, with the class Haplorthod,
coarse loamy over sandy, skeletal mixed mesic (Schlichte, 1968). The soil
profile description is:
Horizon
Litter
A
4-0 cm
(1.5-0 in.)
0-15 cm
(0-6 in.)
15-60 cm
(6 to 24 in.)
60+ cm
(24+ in.)
Description
Very dark grayish brown (10 YR 3/2) loose or
very friable matted layer of forest litter.
Strongly acid (pH 5.6).
Pale brown or brown (10 YR 6/3, brown, 10 YR
4/3 moist) loose gravelly sandy loam.
Structureless and with included hard rounded
shot cemented with iron oxides.
Light yellowish brown (10 YR 6/4, dark
yellowish brown, 10 YR 4/4, or yellowish
brown, 10 YR 5/4 moist) gravelly sandy
loam with less shot.
Light yellowish brown, light brownish-gray,
gray with dark gray gravel, sand and
cobbles, loose and porous, poorly sorted
and somewhat stained with brown and reddish
brown.
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Figure 1. The Everett soil series is an immature,
slightly podzolic soil developed on
loose, poorly sorted glacial outwash.
-------
The following lists the soil density, the percent larger than 2 mm(0.08in)
fraction, and percentage of sand, silt and clay for the Everett soil.
Depth
(cm)
0-15
15-30
30-60
60 +
Density
(g/cm3)
0.71
1.46
1.65
1.74
% Larger
Than 2mm
82
80
84
95
Texture of the 2rnm Fraction
Sand
'
62
72
80
88
Silt
Percent
31
23
16
9
Clay
7
5
5
3
THE MASHEL SOIL SERIES
The Mashel series consists of deep, moderately well drained soils formed
in glacial till. Mashel soils occur on uplands with slopes of 5 to 65 percent.
Elevations range from 210 to 550 m (700 to 1800 ft.). Mean annual precipita-
tion is about 22 cm (55 in.). Mean annual air temperature is about 9°C
(49'°F). The taxonomic class is a fine, halloysitic, mesic Ultic Haploxeralfs.
(Colors are for moist soil unless otherwise noted.)
Horizon
Litter
A
Depth Description
8-0 cm Partially decomposed roots, leaves and twigs,
(3-0 in.) 0 to 8 cm (0 to 3 in.) thick.
0-20 cm Dark brown (10 YR 3/3) loam, brown (10 YR
(0-8 in.) 5/3) dry; moderate fine and medium sub-
angular blocky structure; slightly hard,
friable, slightly sticky and slightly
plastic; 1 percent hard rounded pebbles;
many fine pores, very strongly acid (pH
5.0); clear smooth boundary, 13 to 23 cm
(5 to 9 in.) thick.
20-41 cm Dark brown (10 YR 4/3) heavy loam, pale
(8-16 in.) brown (10 YR 6/3) dry; few faint dark brown
mottles; moderate medium subangular blocky
structure; hard, firm, slightly sticky and
slightly plastic; 1 percent hard rounded
pebbles; many fine and medium roots; many
fine pores; thin patchy clay films on some
faces of peds; very strongly acid (pH 4.7);
clear wavy boundary, 15 to 23 cm (6 to 9
in.) thick.
41-90 cm Yellowish brown (10 YR 5/4) clay loam, light
(16-36 in.) yellowish brown (10 YR 6/4) dry; common
bleaches silt and sand particles on faces of
some peds and within some peds; moderate
medium and coarse subangular blocky structure;
hard, firm, sticky and plastic; 2 percent
-------
...... strongly weathered rounded gravel, less than
1 percent hard pebbles; common fine and
medium roots; common fine and medium pores,
many thin to moderately thick dark brown clay
films on faces of peds and in pores; few
black stains; very strongly acid (pH 4.5);
; gradual wavy boundary, 25 to 56 cm (10 to 22
in.) thick.
Forest vegetation is dominantly western red cedar with some western hemlock.
Subordinate vegetation is sword fern. The site is characteristically wet
throughout the year.
THE WILKESON SOIL SERIES
The soils of the Wilkeson series are deep, well-drained soils formed in
materials weathered from andesite and basalt. They are on slopes of the foot-
hills. Mean annual precipitation is about 203 cm (80 in.) and mean annual
air temperature is about 8 °C (49 °F) The taxonomic class is Eutric
Glossoboralfs; fine loamy, mixed family. (Colors are for moist soil unless
otherwise noted.)
Horizon
Litter
A
Depth Description
5-0 cm Partially decomposed needles, leaves, twigs
(2-0 in.) and roots.
0-10 cm Very dark grayish-brown (10 YR 3/2) gravelly
(0-4 in.) silt loam, grayish brown (10 YR 5/2) when
dry; weak, very fine, subangular blocky
structure; slightly hard, friable, slightly
sticky and slightly plastic; common very fine
roots; 25 percent shot and angular pebbles;
medium acid (pH 5.6); abrupt, smooth boundary,
7 to 13 em (3 to 5 in.) thick.
10-69 cm Dark brbwn (10 YR 3/3) gravelly silt loam,
(4-27 in.) brown (10 YR 5/3) when dry; weak, fine, sub-
angular blocky structure; slightly hard,
friable, slightly sticky and plastic; many
fine, medium and coarse roots; 30 percent
shot and angular pebbles; strongly acid
(pH 5.4); diffuse wavy boundary, 13 to 18 cm
(5 to 7 in.) thick.
70-90 cm Yellowish-brown (10 YR 5/4) gravelly silty
(27-36 in.) clay loam, light yellowish-brown (10 YR 6/4)
when dry; moderate, medium, prismatic,
parting to moderate, medium, subangular
blocky structure; hard, firm,' sticky and
plastic; few fine and coarse roots; common
-------
very fine and fine pores; moderate thick
clay film in fine pores; 10 percent angular
pebbles; medium acid (pH 5.8); gradual, wavy
boundary, 20 to 38 cm (8 to 15 in.) thick.
The forest stand was predominantly old growth western hemlock with a few
young hemlock in the understory. Subordinate vegetation was a mixture of
salal, red huckleberry and some grass species. The area of plot study was
generally open as shown in Figure 2.
-------
Figure 2. Plots on the Wilkeson soil were in an old growth
western hemlock stand with larger older trees'
and an understory of young hemlock. The plywood
box contains the sample collection bottles for
the lysimeter plates.
-------
Section 3
METHODS OF PLOT LAYOUT, SOIL SAMPLE AND ANALYSES
Study methods used for soil sampling and analyses, plot layout, etc. are
conventional and accepted for similar phases of field forestry research.
They involve the establishment of plots in the forest stand and random samp-
ling of the forest soils. Tests of methods of sludge application resulted
in design of an irrigation system for applications of sludge to experimental
plots.
PLOTS ON THE EVERETT SOIL SERIES
Experimental plots were established on Weyerhaeuser Company land on the
west edge of Pack Forest in Section 29, Township 16N, Range 4E, the Willamette
Meridian (latitude 46° 50' W; longitude 122° 22' N). The elevation of plots
on the Everett soil series is 230 m (750 ft.) above mean sea level. The
bench (outwash on which the plots were located) breaks about 60 m (200 ft-.)
west of the plots, dropping steeply into the Nisqually River.
Plots on the Everett soil series were the most intensively studied. The
first study phase developed a method of sludge application, and later phases
studied forest growth rates and biological decomposition.
The forest stand was second growth Douglas-fir established in 1939 with
an average density of 1580 trees per ha (640 stems per ac.) and average basal
area of 35 sq. m per ha (150.7 sq. ft. per ac.). A few survivors of the old
growth forest occurred randomly throughout the plot area. The understory
consisted primarily of salal, Oregon grape and elderberry. Mosses and lichens
are also numerous as soil cover and on downed organic materials (Figure 3).
Two areas were selected on the Everett soil series; one for initial
testing of methods of sludge application, and the second for detailed studies
of soils, soil solution chemistry* decomposition and forest growth as per the
objectives. Square plots (0.04 ha or 0.1 ac.) were established using compass
and tape for measurement of distances and angles. Three plots were estab-
lished for testing methods of sludge application. Seventeen additional 0.04
ha (0.1 ac.) plots were established for testing rates of sludge application
on soils, decomposition and impacts on forest growth rates.
Responsibility for assessment of effects of sludge applications on
forest growth was assumed by the Weyerhaeuser Company as a cooperator. All
trees in each plot were numbered with aluminum tags and measured for diameter
breast height (DBH) to the nearest 0.25 iron (0.01 in.). Increment cores
10
-------
Figure 3. The Everett soil supports a 36-year old Douglas-fir
stand with an average of 1580 trees per ha. Stand-
ing dead trees and cull hardwoods were removed from
the plot (pile,in lower righthand corner).'
11
-------
were taken from dominant and co-dominant Douglas-fir to develop regression
equations which estimated the previous rate of basal area growth. Stand
biomass was estimated by DBH regressions (Dice, 1970) after testing the
equations with additional trees.
The general layout of intensive studies on Everett plots is shown in
Figure 4. Lysimeters were installed to sample volumes and chemistry of soil
water under the forest floor at the boundary between the A and B horizons
(15 to 25 cm or 6 to 10 in.) and the boundary of the B and C horizons (46 to
60 cm, or 18 to 24 in.). Lysimeters were also installed at a depth of 210 cm
(7 ft.) below the C horizon. A continuous vacuum was maintained on each
lysimeter at 0.1 atmospheres (3 in. or 76 mm of mercury) which approximates
the tension of retention of gravitational water in the Everett soil matrix. A
pressure sensitive switch operates on a central vacuum system activating the
vacuum pump automatically to maintain constant tension on all lysimeters.
Extracted soil water samples identified by plots and depths were taken to the
lab at the University for analyses.
Pretreatment sampling of the forest soil by plots was made at the time
of lysimeter plate installation. The forest floor and soil horizons were
sampled for physical properties and chemical constituents.
SOIL SOLUTION MONITORING
A Metro-Data 616 data logger was coupled in the lysimeter soil water
flow system with probes for field recording of pH, dissolved oxygen., .conduc-
tivity and temperature of extracted soil water plots and at varying soil
depths. These probes were scanned at frequent intervals depending on sludge
applications or the dynamics of climatic events. Intermittent 'measurements
for the above parameters of soil water extracted were taken with routine
instrumentation to verify the accuracy of the recorded data. :
Volumes of soil solution collected for laboratory analyses varied
seasonally with rainfall; therefore, in calculating nutrient flux, irrigation
and precipitation were assumed to be uniform over plots and infiltrated and
percolated to sampled depth. Total flux of water was calculated for a given
sample period including a correction factor for seasonal evapotranspiration.
Chemical concentrations were averaged for a particular sampling period and
then used in the determination of a nutrient flux. It should be noted that
years 1, 2 and 3 are TO, 10 and 7 months, respectively.
Analyses for biological components (bacteria and virus) and heavy metals
also were based on soil solution chemistry as monitored by lysimeter extracts
for various soil horizons by plots.
SAMPLING FOR GROUND WATER NUTRIENTS
Wells were drilled as located in Figure 4 to study the chemistry of
ground water adjacent to sludge treated plots. The glacial outwash over-
burden in the plot locations was approximately 10 m (33 ft.) thick overlying
a relatively impermeable lacustrine substrata. Natural flow of water perco-
lates through the Everett soil to the lacustrine outwash interface, then
12 >;v
-------
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s-
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-------
moves laterally to a number of springs on the slopes to the Nisqually River.
Both the springs and water samples from the wells were monitored to assess
impacts of sludge application on ground water chemistry.
Four wells were drilled to depths of 10+ m (33+ ft.). The Wells were
lined with 15 cm (6 in.) inside diameter PVC pipe and tops covered. Ground
water samples were obtained by lowering sample containers into the free water
and extracting a sufficient volume for total chemical analyses. Wells 1 and
2 provided a stable supply of water for chemical analyses. Wells 3 and 4
were frequently dry during drier periods, supplying only water during wet
winter periods. The rates of flow of ground water through the well could not
be measured; consequently, a measurement of nutrient flux in ground water was
not possible. Only changes in concentration of ground water over time are
reported.
14
-------
Section 4
SLUDGE TREATMENTS TO PLOTS
The area of Weyerhaeuser forest land used for the testing of liquid
digested sludge application was based on plot size spacing, proximity to an
access road, and maximum replications possible within the constraints of
transport of large quantities of sludge from Metro's West Point plant to
Pack Forest. The plots were laid out with buffer strips separating different
sludge treatment applications and the water only and control plots Figure 4
shows the relative location of all plots on the Everett soil, the swimming
pool sludge storage tank and pump house, and location of wells for sampling
of ground water.
The initial study of the methods for liquid sludge application used
plots 15, 16 and 17 (Figure 4) which are actually more remote from the study
area than indicated. Plot 15 tested trickle sludge applications; 16 was
under-the-canopy on 1.5 m (5 ft.) risers; and 17 was over-the-canopy on 9 m
(30 ft.) risers.
The experimental design used duplicate plots with 100, 200 and 300 metric
^ns-^r^a per yr' of Slud9e application. Plots 1 and 2 are referred to as
the 100 (100 mt/ha/yr or 44.5 t/ac/yr) series; 4 and 5 as the 300 (300 mt/ha/
yr or 133.6 t/ac/yr) series; and 7 and 8 as the 200 (200 mt/ha/yr or 89 t/ac/
yr) series. Plots 3 (100W), 6 (300W), and 9 (200W) each received 1.3 cm
(0.5 in.) of irrigation water after the sludge application. Plots 10 and 11
received 1.3 cm (0.5 in.) of irrigation water only per inch, while plots 13
and 14 are untreated control plots.
Recognition of the need to reduce sludge application rates in the second
year of study resulted in the establishment of plots with sludge application
rates of 10, 20, 30 and 40 mt/ha/yr (4.5, 8.9, 13.3 and 17.8 t/ac.). These
duplicate plots are identified as plots 24, the 10 series; plots 23 the 20
series; plots 22, the 30 series; and plots 21, the 40 series (Fig. 4).
PLOTS ON MASHEL AND WILKESON SOILS
The sludge study on the Mashel and Wilkeson soils was limited to the
effects of sludge applications on soil solution chemistry. This investiga-
tion required a smaller plot area, reducing the problem of logistics for
sludge transportation and applications.
Sludge was transported from the. receiving area at the Everett plots to
the sites of Mashel and Wilkeson soils on Pack Forest. Duplicate 0.01 ha
plots (0.025 ac.) were established on a uniform slope to receive applications
15
-------
of 10, 20, 30 and 40 mt/ha/yr (4.5, 8.9, 13.3 and 17.8 t/ac.). lysimeter
plates were installed in a manner similar to that of the Everett plots to a
depth of 60 cm (24 in.), a zone midway in the B horizon. As with the
Everett plots, lysimeters were placed under the forest litter layers and at
the interface of the A and B soil horizons. Soil solution sampling and soil
chemistry were similar to those methods used on the Everett plots.
16
-------
Section 5
ANALYTICAL ANALYSES OF SOILS, SOIL SOLUTIONS AND GROUND WATER
Soil pits excavated to the C horizon for lysimeter installations were
sampled in duplicate by horizons, establishing pretreatment exchangeable and
total soil chemistry. Post sludge treatment soil samples were taken from
new pits in a similar manner. Soil samples were air dried, then sieved for
the less than 2 mm (.08 in.) fraction prior to analyses.
SOIL PROPERTIES
Soil pH was determined with a glass electrode on a solution of 1:1 soil
to distilled water, allowing time to come to equilibrium. Litter layers were
mixed with a 1:2 ratio water (Forest Soils Committee, 1953).
A modified Kjeldahl method was used to determine total soil nitrogen.
The form of most nitrogen in forest soils is protein as ami no acid groups
attached to carbon. Organic matter is oxidized in concentrated sulfuric
acid, a slow reaction catalyzed by selenium and additions of sodium sulfate.
After digestion, the solution is made strongly basic and ammonia distilled
into a dilute acid. Titration of the distilled solution with a standard
determines the amount of ammonia absorbed (Breraner, J. M., 1965).
Soil organic material was determined by the modified wet combustion
method (Walkley and Black, 1934). Soil samples are treated with an excess of
oxidizing agent, sulfuric acid in chromic acid. Excess chromic acid is
determined by a back titration with a standard ferrous sulfate solution.
Heat of dilution from added concentrated sulfuric acid speeds the reaction.
Chromic acid is not carbon specific but will react with any readily oxidiz-
able substance. Approximately 77% of the total carbon in soil organic
matter is oxidized. Approximately 58% of soil organic matter is carbon.
*
Total cation exchange capacity for soil samples was determined by
leaching samples with normal ammonium acetate buffered to neutral pH
(Jackson, 1958). Determination of cation exchange capacity involves satur-
ating the soil colloidal exchange .complex with a known cation (NHJ and will
exchange cations on the soil exchange complex. Displacing NH, cations by
another leaching solution (Na) allows determination of total soil cation
exchange capacity as mi Hi-equivalents per 100 grams of oven dry weight of
soil (meq/lOOg O.D. soil).
The ammonium acetate solution containing the original displaced cations
from the soil sample is analyzed for exchangeable cations (Ca, Mg, K and Na),
17
-------
which are also expressed as meq/lOOg O.D. soil. The sum of exchangeable
cations divided by the total cation exchange capacity is termed 'base
saturation1 and expressed as percent.
Total chemistry of soils required digestion until dry (overnight) of a
soil sample in a nitric-hydrofloric and hydrofulvic acid mixture (Jackson,
1958) in teflon beakers. The residue is then redissolved in distilled water
and the solution analyzed for cations on the atomic absorption spectro-
photometer. Pretreatment total soil chemistry values were used to define
the statistical confidence intervals. Variability in total chemistry was
high because less than 0.15 g of soil was digested. There are also large
differences in actual soil particle sizes which make up the 0.15 g sample.
It is assumed that chemical composition of less than 2 mm (0.08 in.) fraction
is similar to the greater than 2mm (0.08 in.) fraction.
Carbon-nitrogen ratios are calculated from the average values for soil
organic matter and total nitrogen. Organic matter is assumed to consist of
58% organic carbon. Dividing the percentage of soil organic carbon by the
percentage of total nitrogen gives the carbon-nitrogen ratio.
SOIL SOLUTION AND GROUND WATER ANALYSES
Soil solution and ground water samples were transported to the University
of Washington lab. One subsample is filtered through Whatman 1 filter paper
and digested with sulfuric acid and hydrogen peroxide for total Kjeldahl
nitrogen and total phosphorus determinations. Another subsample is filtered
through Whatman glass fibre paper and used for anion and cation determina-
tions. The remaining sample is used for pH measurement, alkalinity titration,
conductance and TOC. All samples are stored at 2-4° C (36-39° F).
Total Kjeldahl nitrogen and total phosphorus are determined by a modi-
fied Kjeldahl (Standard Methods, 1971) which converts most forms of organic
nitrogen and phosphorus into ammonium and phosphate. Ammonium and phosphate
are then determined by Auto-analyzer methods. Total Kjeldahl nitrogen,
nitrite and nitrate nitrogen are summed as total nitrogen. The difference
between total Kjeldahl nitrogen and ammonium nitrogen is organic nitrogen.
Ammonium nitrogen (NH.-N), nitrate nitrogen (N03-N), total Kjeldahl
nitrogen (Total N), phosphite phosphorus (P04P), total phosphorus (Total P),
and sulfate sulfur are determined by use of a Technicon Autoanalyzer II.
NH^-N is determined according to Technicon Industrial Method No. 108-71W/
Preliminary. Ammonium in the prepared sample is complexed with sodium
phenoxide followed by sodium hypochlorite resulting in a blue indophenol-type
compound, which is determined colorimetrically and is directly proportional
to the ammonium nitrogen concentration (NH^-N).
NOjjN is determined according to Technicon Industrial Method No. 158-70W/
Preliminary. Nitrate is reduced to nitrite in a copper-cadmium column.
Reaction with sulfanilamide and coupling with N-l napthylethylene-diamine
dihydiochloride produces a red compound which is measured colorimetrically.
This method determines nitrite as well as nitrate nitrogen, but nitrite
concentration in these water samples is assumed to be negligible.
18
-------
Phosphate phosphorus is determined according to Technicon Industrial
Method No. 155-71W. Phosphate reacts with ammonium molybdate in the pre-
sence of ascorbic acid and antinomy to form a blue phosphomolybdenum complex
which is measured colorimetrically. This method determines only ortho-
phosphate but contribution from other forms is negligible.
Sulfate sulfur is determined according to Technicon Industrial Method
No. 226-72W. Interfering cations are first removed by a cation exchange
column. Sulfate is then reacted with barium chloride. Excess barium forms
a blue chelate with methy!thymol blue, which is measured colorimetrically.
Calcium, sodium, potassium, and magnesium are determined by atomic
absorption spectrophotometry using an Instrumentation Laboratory Model IL 353
atomic absorption spectrophotometer. Procedures described by the manufact-
urer are used (Procedure Manual for Atomic Absorption Spectrophotometry,
Instrumentation Laboratory, Inc.).
Soil solution pH is determined using a Radiometer model 26 pH meter by
methods outlined in Standard Methods (1971) and manufacturer's instructions.
Total alkalinity is determined by an automated titration procedure (Standard
Methods, 1971) with a Radiometer model II titrator and model II autoburette
in conjunction with the pH meter, according to manufacturer's instructions.
Conductivity is measured using a YSI model 31 conductivity bridge according
to manufacturer's instructions and Standard Methods (1971). Chloride is
determined on a Technicon Autoanalyzer II according to Technicon Industrial
Method No. 99-70W Preliminary.
VIRUS DETERMINATION
Soil and soil water samples were analyzed for virus and certain bacteria
by the Virology Lab. at the Children's Orthopedic Hospital, Seattle.
Soil and water samples were incubated at 35-36° C(.95-97°F). for 2 weeks on a
variety of cell lines to test for viruses. These cell lines included African
Green Monkey, Rhesus Monkey Kidney; Heteroploids Hep II and HL; and Diploid,
Human Embryonic Tonsil. Presence of enteric viruses was determined by cyto-
pathetic effects on cell deformations (Lenette and Schmidt, 1969 or minor
modifications).
TOTAL AND FECAL COLIFORM DETERMINATIONS
Coliform analyses were provided by Metro. Soil and water samples were
tested for presence of total and fecal coliforms. Samples were incubated 24
hours on a lactose broth as a presumptive test. Transfer to brilliant green
lactose bile broth and continued incubation was the confirmed test. Gas
production in fermentation tubes is the positive visual interpretation of
coliform presence. Dilution tubes offer an estimate of the most probable
number (MPN) per sample volume (Standard Methods, 197,1).
19
-------
Section 6
TOTAL ORGANIC CARBON COMPONENTS
The majority of organic carbon analyses measures humic and fulvic acid
fractions (Schnitzer and Kahn, 1972; Goring, 1972; Gieseking, 1975). Organic
molecules smaller than fulvic acids in forest soils have received less atten-
tion but are of concern in sludge studies, since refractory organic compounds
such as pesticides are in this classification. Organic compounds are isola-
ted by extraction with solvents such as ether, chloroform and methanol
(Braids and Miller, 1975). Identiftcatipn of extracted organic materials is
done in several ways: chromatographic separation by gas, thin layer or gel
filtration chromatography in combination with spectral identification.
Soil samples were extracted by redistilled ether saturated with water
and sodium chloride in a stoppered erlynmeyer flask and gently shaken for 42
hours. The ether extract was decanted, dried with magnesium sulfate, and
concentrated on a rotoevaporator. For gas chromatographic analysis, diazo-
methane was added to the sample to make methyl esters or free acids, accord-
ing to directions from Aldrich Chemical Company.
TOTAL ORGANIC CARBON MEASUREMENTS
Total organic carbon measurements were made on a Dohrmann-Envirotech
DC-50 TOC analyzer. The unit receives a 30-microliter injection of acidified
(pH 2) aqueous sample in a platinum boat containing manganese dioxide as an
oxidation promoter. The boat is moved into a 90°C(194°F) zone where volatile
carbon and C02 are removed. Volatile carbon components are trapped on a
column of Porapak Q, while the C0£ is vented. The column is heated and back-
flushed. Volatile organics are burned to C02- Residual organic*; in the boat
are then moved to an 850° C(156QOF) zone where they are burned to C02-
Measurement is done by passing the 0)3 from pyrolsis over a Ni catalyst
in a hydrogen-rich atmosphere. The CO? is reduced to methane, then bubbled
through a humidifier and burned in a flame ionization detector. Response of
the flame detector is integrated so total mg/1 or ppm of carbon are read
directly from the instrument.
Gas Chromatography
A Perkin-Elmer model 990 gas chromatograph with flame ionization detec-
tion was used. Two columns were used with the following conditions:
20
-------
Column 1
SCOT
15.2 m (50 ft.)
200° C. (392° F.)
200° C. (392° p.)
x 40
DEGS
90°-180° C. (194-356° F.)
40 C./min. (7.2° F/min.)
1 min.
10/1
.2 1
5.5 ml/min.
Column 2
SCOT
15.2 m (50 ft.)
275° C. (527° F.)
300° C. (572° F.)
x 80
DEXSIL-300
1800-2700 C. (356-518° F.)
6° C./min. (11° F/min.)
1 min.
10/1
.2 1
5.5 ml/min.
Column type
Column length
Injector temp.
Manifold temp.
Attenuation
Column phase
Program
Rate
Initial
Split ratio
Injection volume
Flow
Mass Spectrometry
The gas chromatograph was connected to a Perkin-Elmer Hitachi RMS-4 mass
spectrometer. The units are interfaced with a gold jet separator with other
connections being gold or glass. lonization voltages were normally 70 ev.
Output was achieved through a B&F oscillograph, model number 3006.
Gel Filtration Chromatography
Sephadex G-75 gel with a solvent of 0.01 N HaOH was used for gel filtra-
tion work. A chromatronix CMP-1 pump was used for solvent delivery. Injec-
tion into the system was through a valve and sample loop. Detection was done
with ultraviolet detectors at 254 mm, (.10 in.). The columns were 100 cm' x 6 m
(39.4 in. x 0.24 in.) glass with chromatronix teflon fittings. Typical
conditions were:
Solvent
Temp.
Flow
Sample size
Chart speed
Recorder
Detector
Wave length
Attenuation
F.)
System 1
0.01N NaOH
22.5° C. (72°
6 ml/hr.
1 ml
1.5cm/hr. (0.6 in./hr.)
Varian A-25
Chromatronix
254 mm (10 in.)
0.04
System 2
0.01N NaOH
22.8° C. (73° F.)
11.8 ml/hr.
1 ml
1.5 cm/hr. (0.6 in./hr.)
ISCO, UA-5
ISCO, UA-5
254 mm (10 in.)
0.05
Using gel filtration chromatography, the largest molecules are eluted
first, with the smaller molecules later. This assumes small interactions
between the column packing and the organics being analyzed.
21
-------
Section 7
BIOLOGICAL DECOMPOSITION
Wood stakes (1 x 4 cm or 0.4 x 1.6 in.) prepared from sapwood of
Douglas-fir (American Standard Testing Methods ASTM D1758-60T) were coded
with a permanent identifying number and dried to a constant weight at 105° C
(220° F) in a forced air oven (referred to as oven dried weights). Within
the designated treatment plots, the stakes were placed at the following
positions in the soil profile: 1) surface of the litter; 2) 1 cm (0.4 in.)
below the litter; and 3) 10 cm (3.9 in.) below the litter layer. Five
replicas of 10 stakes were placed at each position at the initiation of the
test treatments. Representative wood stakes set aside as standard samples
were stored in. capped glass jars until needed for analysis.
At the prescribed sample time, one group of 10 stakes was recovered from
the designated treatment site and soil profile positions. In the laboratory,
extraneous debris clinging to the outside of the stake, such as soil par-
ticles, were removed. Immediately thereafter, the code number was recorded
along with the wet weight of each stake. Samples were then oven dried at
105° C (220° F) for 24 hrs. and cooled in a vacuum desicator.
DECOMPOSITION ANALYSES
The percent stake moisture and weight losses were individually determined;
from the oven dry weight as follows:
Moisture content -
x 100
Weight loss
= initial oven dry weight - final oven dry weight
final oven dry weight
,QO
1% Sodium Hydroxide Solubility
Solubility of wood in one percent sodium hydroxide, a measure of cellu-
lose decomposition, was determined following the procedures of TAPPI Standard
Methods (T4m-59) as modified by Cowling (1962). Stakes were ground in a
Wiley mill until they passed through a 40-mesh screen (TAPPI Tllin). Repli-
cates from each treatment and profile position were combined to make a single
sample.
One gram of the ground sample was added to a tared tall form 200 ml
(6.8 oz.) Pyrex beaker. The sample was returned to the oven and its oven
dry weight determined. To the beaker, 50 ml (1.7 oz. ) of standardized 1%
22
-------
sodium hydroxide were added. The beaker was
placed in a boiling water bath for one hour.
was stirred to facilitate digestion.
covered with aluminum foil and
Every 15 minutes, the mixture
Digested samplers were suction filtered using a tared cintered glass
crucible of medium porosity. Quantitative transfer of the digestion mixture
,.,ao a/^mni,-.^,! k,, using two 50 ml (Ii7 ozj aiiqUots of hot distilled water
Next, the sample was washed with 50 ml (1.7 oz.) of 10%
from the residue. The crucible and contents were
(220° F) oven for 48 hours, cooled in a vacuum desicator
was accomplished by
to rinse the beaker
glacial acetic acid
removed to a 105° C
and then weighed.
Solubility was expressed as a percentage of the moisture-free weight of
the loss during digestion. Relative solubility was computed by comparing the
solubility of untreated, unexposed stored standard samples with that of the
treated sample as follows:
Relative solubility =
100 x solubility treated sample - solubility of untreated similar wood sample
solubility of untreated similar wood sample
Above procedures are routine for analyses of biological decomposition of
wood samples as per procedures of Minyard and Driver (1975).
23
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Section 8
EVALUATION OF TREE GROWTH
The Weyerhaeuser Company used the twelve 0.04 ha (0.1 ac.) plots for
forest growth rate research. Growth plots coincided with sludge treatments
identified in Figure 4; All dead trees and cull hardwoods were felled and
piled outside of the plot area. Remaining trees were tagged by number at
1 2 m (3.9 ft.) above the ground line. Diameters of each tagged tree were
measured at DBH (1.4 m or 4.5 ft.) and identified by a paint mark. Total
tree heights were measured to the nearest 0.3 m (1 ft.) on 7 trees in each
plot plus 5 additional trees to complete the range of diameters encountered.
Increment core borings were taken from 10 trees per plot to assess the past
growth rates.
Analysis of tree growth rates tested changes in diameter growth, basal
area and volume of individual trees within each treatment by the following
regression models.
b (DBH70)
b [(DBH75 - DBH70) / 5]
b [(DBH75 - DBH70) / 5]
b (BA70)
b [(BA75 - BA70) / 5]
b [(BA75
1.
2.
3.
4.
5.
6.
7.
8.
(DBH75 -
(DBH76 -
(DBH77 -
(BA75 -
(BA76 -
(BA77 -
(Volume
(Volume
DBH70) / 5 = a
DBH75) / 2 = a
DBH75) / 3 = a
BA70) / 5 = a
BA75) / 2 = a
BA75) / 3 = a
76 - Volume 75)
77 - Volume 75)
BA70) / 5]
= a + b (Volume 75)
= a
+ b (Volume 75)
Where DBH 75 is the diameter of the tree in 1975, likewise DBH 70 would
be the diameter in 1970. BA 75 is the basal area of the plot in 1975 and
volumes are spelled out.
Slopes of regression lines for each treatment were compared to the slope
of the unirrigated control using a "t" test.
where
B
3o
SE-
SE;
slope of treatment
slope of unirrigated control
standard error of treatment slope
24
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to test the null hypothesis that there were no differences in growth between
each treatment and the control. A simple one-day analysis of variance DBH
growth was conducted also with those plots that had replications to test for
treatment effects.
A final analysis arrayed all trees by pretreatment diameter and periodic
annual increment (pal). From this list, trees were selected and paired with
each sludge treatment and with the control. Paired trees had equal pai and
approximately the same initial DBH. Changes in growth rate were analyzed by
DBH, basal area, and volume testing the sludge treated trees against equiva-
lent control trees.
25
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Section 9
LIQUID WASTE PROCESSING AND SLUDGE PROPERTIES
Metro serves approximately a million residents plus industry in the
Greater Seattle area for treatment of domestic and industrial waste liquids.
Several smaller outlying communities provide primary and secondary waste
treatment; however, residual sludge solids are pumped to and stabilized at the
Metro West Point plant. Over the year, average daily flow into the treatment
plant at West Point is 475 million liters (125 million gallons) of raw sew-
age. Portions of the Metro sewer system are still combined, mixing municipal-
industrial effluents with urban runoff. Large seasonal variations occur in
volumes of effluent treated and the ratio of solid-organic constituents.
Anaerobic digestion reduces solids by 40% in an average digestion time of
21 days. Residence time in the digesters ranges from 14 to 35 days, dependent
upon volumes of input to the plant. These conditions cause highly variable
sludge composition over time. Average daily solids production over the year
is 50 metric tons (55 tons) on a dry weight basis.
Treated sludge was discharged into Puget Sound through a deep water dis-
sipator pipeline until the 1972 amendments to the Federal Water Pollution
Control Act. The Clean Water Amendments banned discharges of solids but
allowed continued discharges of primary treated waste waters. Sludge dewater-
ing facilities were installed at West Point plant to facilitate sludge dis-
posal as a dewatered cake. Dewatering-and disposal are very expensive, „
leading to consideration of alternatives such as sludge irrigation for disposal
at lesser costs and with possible benefits as a fertilizer and water supple-
ment.
Liquid digested sewage sludge (3-7% solids) is trucked from West Point to
Pack Forest (approximately 110 km or 70 mi.) in a closed 19,000-liter (5000-
gal.) tanker. Sludge may be applied directly or diluted with river water to
provide a sufficient volume at the design concentration to irrigate all plots
on a weekly basis (Fig. 5).
CHEMICAL COMPOSITION OF SLUDGE
Table 1 summarizes maximum, minimum and average concentrations of various
constituents in Metro sludge applied to research plots. Total solids are the
oven dry product of evaporation of a given quantity of liquid sludge. Total
nitrogen, phosphorus and heavy metal constituents are determined as portions
of the dried sludge. Other chemical constituents are determined on sludge
and makeup water.
26
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Table 1. MAXIMUM, MINIMUM AND AVERAGE COMPOSITION OF
SEWAGE SLUDGE APPLIED TO PLOTS
Component
All values percent (%)
Total Solids
Calcium
Magnesium
Potassium
Sodi urn
All values parts per million
Total Nitrogen
NH4-N
N03-N
Total Phosphorus
Orthophosphate
Zinc
Copper
Chromium
Lead
Cadmi urn
Mercury
Minimum
2.10
2.40
0.50
0.15
0.32
(ppm)
945
674
120
625
150
2,200
900
500
240
50
7
Concentration
Maximum
3.40
3.20
0.70
0.48
0.76
1,860
1,090
135
922
900
3,100
1,200
800
400
62
12
Average
3.20
2.64
0.55
0.29
0.51
1,600
895
131
900
850
2,740
1,020
620
356
55
11
27
-------
Total solids varied from 2.1 to 3.4% averaging 3.2%. Total nitrogen
ranged from 945 to 1860 parts per million (ppm) with an average of 1600 ppm.
The NH4~N component of-total nitrogen dominated and ranged from 674 to 1090
ppm with an average of 895 ppm. Nitrate levels remained fairly constant
ranging from 120 to 135 ppm with an average of 131 ppm. Of the total phos-
phorus (625 to 922 ppm), orthophosphate was the dominant form (150 to 900
ppm). Quantities of orthophosphate were more variable than total phosphorus
with an average of 900 ppm for total and 850 ppm for orthophosphate.
Limited determinations were made for the heavy metals, zinc, copper,
chromium, lead, cadmium and mercury. Large concentrations of zinc found in
Seattle's municipal sludge indicate the probable contribution of industrial
zinc plating and galvanizing processes. Zinc concentrations are relatively
constant ranging from 2200 to 3100 ppm with an average of 2740 ppm. In a
like manner, copper concentrations are also fairly constant ranging from 900
to 1200 ppm, averaging 1020 ppm. Chromium averaged 620 ppm with a range of
from 500 to 800 ppm. Lead occurs in reduced amounts averaging 356 ppm with
a range of 240 to 400 ppm. Concentrations of cadmium were fairly constant
with an average of 55 ppm and a range of 50 to 62 ppm. Mercury occurred in
relatively low concentrations, usually around 11 or 12 ppm and occasionally
7 ppm.
The concentrations of calcium, magnesium, potassium and sodium are
sufficiently large to report their values as a percentage. Calcium concen-
trations are large ranging from 2.4 to 3.2%, averaging 2.64%. Magnesium
averages about 20% of that of calcium with an average of 0.55%, ranging from
0.5 to 0.7%. Potassium occurs in minimum concentrations for this group of
elements, averaging 0.29% and ranging from 0.15 to 0.48%. Sodium concentra-
tions are quite similar to magnesium averaging 0.51% with a range of 0.32 to
0.76%.
28
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Section 10
STUDY OF SLUDGE APPLICATION METHODS
Initial calculations for proposed rates of sludge application were made
for the plots on Everett soils on Weyerhaeuser Company lands. The proposed
weekly application rates required transport of 38,000 1(10,000 gal) of (Fig. 5)
liquid sludge per week from West Point to Pack Forest. The irrigation system
used a 91,000 1 (24,000 gal.) storage pond made from a backyard swimming pool
5.5 m (18 ft.) in diameter and 1.4 m (4.5 ft.) deep. A drain from a low spot
in the center of the storage pond led to the pump and PVC piping system,
sprinklers and trickle systems with gate valves and cold weather drains at
spacings necessary to achieve uniform application of sludge over each test
plot. Sludge discharged from the tanker under gravity (Fig. 6).
The system as designed was tested with water for the positioning of
sprinklers as well as the adjustment of sprinkler heads and proper sizing of
the nozzles. The three methods tested were over-the-canopy sprinklers on 9 m
(30 ft.) risers, spray irrigation on 1.5 m (5-ft.) risers, and a uniform
application through a trickle system which consisted of spaced 0.1 cm (0.25
in.) drain holes in PVC piping.. Uniform coverage by sprinkler systems on
plots was achieved by sprinklers placed 18.3 m (60 ft.) apart at corners of
plots with 90° coverage. A series of trials with water resulted in uniform
application of rates of water over areas of the plots.
This irrigation system, as designed by a consultant, had been used
successfully for irrigation water as well as distribution of dairy barn
manures over fields. Sludge, however, is another product and the pump with a
closed impeller plugged immediately with hair and other coarse solids when
attempting to distribute sludge. Few investigators contacted had experience
with the particular problem of uniform sludge application over relatively
small plots. Many investigators had experience with large irrigation canons
used for spreading of a variety of waste material on a large area. Many
systems were easily eliminated with a narrowing to a few pumping systems
which would have the greatest potential for success. A final choice of a
Moyno positive displacement pump (model 2SWG12H-CDQ) was powered by a 3-phase
10-hp motor, operating at 1250 revolutions per minute (rpm). Problems with
the quantities of miscellaneous solids of varying sizes in the sludge required
a pregrinding by a Maz-o-rator before sludge was delivered to the pump. The
Maz-o-rator was also powered by a 10-hp motor operating at 1800 rpm (Fig. 7).
The combination of the Maz-o-rator and Moyno pump required a consider-
able modification of the previously designed electrical system. Power
demands of the 10-hp motor required that each operate on an individual
29
-------
Figure 5. Sludge was transported from Metro's West Point
Plant to Pack Forest in 19,000-liter quantities
(5,000-gal.). Usually two trips were made each
day sludge was applied.
30
-------
Figure 6. A ramp was constructed so the tanker trucks
could discharge sludge by gravity flow to
the storage pond.
31
-------
Figure 7. Adjacent to the storage pond, a small structure
housed the combination Maz-o-rator and Moyno
pump. Piping to the right is the suction line
from the storage pond with the supply lines to
plots underground.
32
-------
switching and circuit system. As the Maz-o-rator initiates grinding and
delivering of material to the pump, the Moyno pump is activated to distribute
the ground sludge material to plots.
The above system very capably delivered sludge to the trial plots.
SPRINKLER MODIFICATIONS
The Maz-o-rator was a very effective grinder of solid materials, plastics,
metals and stiffer paper products. The Maz-o-rator, however, was ineffective
in grinding soft or limp materials, e. g., large quantities of hair. Care in
installation of the plumbing distribution system with pipe connections and
gate valves eliminated rough projections upon which hair would cling. The
Rainbird 65D TNT sprinklers under trial, however, had many rough projections
which retained hair, causing malfunction of the sprinklers. Malfunction
included retention on spray deflectors, giving very poor distribution of
sludge and obstruction of the mechanics of the sprinkler return mechanism
necessary for achieving uniform distribution of sludge over plots. Occasion-
ally, large solids would also obstruct the sprinkler nozzle orifice. The
Rainbird 65D TNT sprinkler has a deflector arm with a lower bar upon which
substantial amounts of hair would collect.
Modifications of the sprinkler head included removal of lower portions
of the deflector arms and increasing the nozzle orifice size to 1.3 cm (0.5
in.) inside diameter. Rough projections on the brass casted sprinkler arm
were ground smooth and the arm teflon coated. These modifications greatly
reduced the accumulations of hair, allowing a uniform sweep and return of
the sprinkler head under operation. Figure 8 shows the modified sprinkler
after a year and a half of sludge applications without cleaning.
33
-------
Figure 8. The Rainbird 65D TNT sprinkler had the lower
deflector arm removed and was teflon coated,
following removal of rough projections in the
brass casting.
34
-------
Section 11
SUMMARY OF TESTS OF SLUDGE APPLICATION METHODS
The aforementioned modifications of the pumping and sprinkler systems
allowed reasonably trouble-free sludge applications over trial plots (plots
15, 16 and 17, Fig. 4). Testing of the three methods of sludge application-
over- the-canopy, spray irrigation and trickle irrigation—took place simul-
taneously with modification of the sprinkler heads.
OVER-THE-CANOPY APPLICATION
Over-the-canopy sludge application was suggested based on possible use of
sludge irrigation through a complete forest rotation. Retention of sludge in
the crowns of young forest trees and certain growth related impacts were of
interest in trial of this application method. It soon became apparent that
problems of cleaning plugged sprinklers on 9 m (30 ft.) risers was a major '
disadvantage of this application method. While risers in the forest crowns
achieved over-the-canopy application, the interference of tree crowns caused
poorer distribution of sludge over plots. Sludge dripping on workers from
the canopy, either following sludge irrigation or during periods of rainfall
at later dates, was also undesirable. Aerosol drift from over-the-canopy
application remains a problem of unknown consequences.
TRICKLE IRRIGATION APPLICATION
The designed trickle irrigation system used perforated PVC pipe with
sufficient 0.6 cm (0.25 in.) holes to achieve uniform distribution during
water trials over the plot. Pressures of less than 1.0 kg/cm2 (15 psi) were
used for tests of sludge application by the trickle system.
Even though topography of test plots was sloped very gently, slight
changes in topography (depressions) caused significant differences in pres-
sure and quantities of sludge applied to areas of the plot. A slight sag in
a pipe would induce a disproportionately large delivery of sludge to the low
spot. Successive plugging of perforations also resulted in great spatial
differences in rates and quantities of sludge applied. Normally occurring
sol id'materials would be,transported to the lowest ends of perforated pipes
where they became plugged preventing the drainage of sludge from the distri-
bution system. A pond of sludge tn the trickle area is shown in Figure 9.
UNDER-THE-CANOPY SPRAY IRRIGATION
Under-the-canopy spray irrigation was much easier to work with and
cleaner than over-the-canopy or trickle systems. Unplugging of sprinkler
35
-------
Figure 9. Heavy rates of sludge application caused impeded
infiltration, resulting in ponding of sludge in
depressions. This example from the trickle
irrigation plot in an area of concentrated sludge
applications.
36
-------
heads on 1.5 m (5-ft.) risers was easily achieved. Distribution of sludge
over the plots was also uniform without problems of sludge drippinq from the
forest canopy. Aerosol drift is also considerably less of a problem as wind
movement under the canopy is significantly reduced.
The major disadvantage of under-the-canbpy distribution is the increased
amount of plumbing and more numerous sprinklers required for uniform unit
area application. A final mode of operation evolved where grinding of sludge
in all seasons of the year is definitely required. Metal bottle caps, all
sorts of plastic, occasional dense hair mass, paper products and organic
materials such as fruit pits are effectively ground to pass the plumbing
system and sprinkler nozzles by the Maz-o-rator. The pumping system requires
about 6.3 kg/cm2 (90 psi) delivered by the pump on fairly level ground
Pressure drops within the pipe system result in, about 2.8 to 3.2 kg/cm2 (40
to 45 psi) delivered to the sprinkler orifice. This pressure is sufficient
to operate the sprinkler efficiently and achieve good distribution of sludge
over the plots. An operating sprinkler is shown in Figure 10.
*u uN?Zzl! Pressure|.of about 3.2 kg/cm2 (45 psi) did not cause damage to
the bole of Douglas-fir when over 3 m (10 ft.) from the sprinkler. Ideally,
sprinklers should be farther from trees as poor distribution results from
trees too close to sprinklers.
Initial rates of sludge application on the Everett plots were 0.6, 1 3
and 1.9 cm (0.25, 0.5 and 0.75 in.) weekly in one short application to
duplicate plots. Irrigation through the large modified nozzles required 4 25
minutes to apply an area depth of 0.6 cm (0.25-In.) to a plot. The experi-
mental design called for a third series of plots to receive an additional
1.3 cm (0.5 in.) of water. This water, in effect, washed off the sludge
from subordinate and forest vegetation and provided an additional quantity of
water to test the impacts of irrigation.
37
-------
Figure 10. Sprinklers were located on 5-ft. risers at each
corner on the square plots.
38
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Section 12
INITIAL SLUDGE APPLICATIONS
Results of certain initial trials and development methods of sludge
application have been summarized in preceding sections. Results described
in the following section are a combination of visual observations of the
physical impacts of sludge application at design rates to particular plots,
as well as analyses of soil solution chemistry.
A range of initial rates of sludge application was calculated to ade-
quately replace soil moisture lost by summer evapotranspiration. Solid load-
ing was projected on the basis of carbon-nitrogen ratios and total chemical
constituents expected in sludge.
SLUDGE APPLICATIONS AND CONSTITUENTS
Solids in sludge received from Metro averaged 3.2% compared to expected
2.1% average. Total nitrogen averaged 1.6% compared to an expected concen-
tration of 0.9%. Average carbon-nitrogen ratio was 11:1, rather than 18:1
as expected.
Even had constituents been as expected, impairment of surface soil
infiltration capacity would have occurred in plots when total applied sludge
equalled about 25.4 cm (10 in.). Reduced infiltration occurred about 12 to
14 weeks after initiation of sludge application for, the heaviest 1.9 cm
(0.75 in.) weekly rates (300 series, 300 mt/ha/yr or 135 t/ac/yr) of sludge
application. Ponding of sludge occurred over 5 to 25% of the plot area (300
plots) by surface flow of sludge from localized spots of impeded infiltration
to low spots or micro-depressions. Sludge applications (300W plots) followed
by 1.3 cm (0.5 in.) of irrigation water had considerably less problems with
impeded infiltration, even at greater sludge application rates. Plots 200
developed similarly impaired infiltration problems as total sludge applica-
tions approached 25 cm (10 in.). Sludge applications were terminated for the
winter in December 1975. Plots 100 and 100W maintained good infiltration
over 98% of the plot area with only very minor ponding occasionally occurring
in low spots. Total application to 100" plots was 12 to 13 cm (4.7 to 5.1 in.).
Undoubtedly, if these coarse textured, gravelly Everett soils developed
impeded infiltration with the 200 and 300 mt/ha (88 and 135 t/ac.) rates of
waste and sewage sludge application originally used, most other forest soils
would develop similar problems at equivalent application rates.
Initial heavy rates of sludge applications (1.9 cm or 0.75 in./wk.)
established the upper limit of sustained short-term (in 12 to 14 weeks)
39
-------
sludge loadings. Impeded infiltration resulted from repeated heavy weekly
applications of sludge which formed a nondrying film over the forest floor.
Applications of sludge to the 100 series plot usually dried before a repeat
application a week later. Short-term sludge applications to the 100 series
plots were about one-half (12 to 13 cm or 4.7 to 5.1 in.) of the maximum
short-term loadings (25 cm or 10 in.). Maximum loading rates have an
economic advantage in that reduced forest areas as well as reduced amounts
of plumbing would be required for maximum amounts of sludge disposal.
Quantities of solid constituents in sludge and the percentage of total nitro-
gen content exceed estimated amounts used in designing initial sludge appli-
cation rates. Nitrogen constituents were double those expected, based on
Metro's chemical analyses, and the heterogeneous quantity and variety of
solid constituents also was much greater than expected.
Large inherent variability in properties of forest soils, along with
variability in sludge chemistry., makes interpretation of significant impacts
of sludge application to soils difficult. When applications of sludge were
terminated in December 1975, it appeared the 100 and 100W (100 mt/ha or
44 t/ac.) treatments were probably approaching the maximum short-term limit
in rate of sludge application. Heavier sludge applications had resulted_in
excess nitrate concentrations in soil solutions. Modified rates of appli-
cation were proposed at 10, 20, 30 and 40 mt/ha (4.5, 8.9, 13.3 and 17.8
t/ac.). On re-initiation of sludge application in 1976, these reduced rates
were used on a series of new plots on the Everett soil and extended to the
Mashel and Wilkeson soils. Applications of sludge continued on the original
plots with the lowest rates (10 mt/ha or 4.5 t/ac.) going on plots which had
received 100 mt/ha/yr (44 t/ac./yr.) rates during the first year. Heavier
applications were applied to those plots which previously had received the
heavier applications—20 mt/ha (8.9 t/ac.) on 200 plots and 30 mt/ha (13.3
t/ac.) on 300 plots.
40.
-------
Section 13
THE IRRIGATION SYSTEM AND SLUDGE APPLICATION RATES
No problems were encountered with Metro's delivery of sludge to the Pack
Forest plots. Tankers unloaded the sludge in the storage reservoir (Fig. 5)
from which it was pumped by the combination Moyno-Maz-o-rator system to
research plots.
The final distribution system for uniform application of sludge to 0.04
ha (0.1 ac.) plots used the modified Rainbird 65D TNT sprinklers with 1.3 cm
(0.5 in.) I. D. nozzle, spaced 18.3 m by 18.3 m (60 x 60 ft.). The combina-
tion grinder (Maz-o-rator) and positive displacement Moyno pump delivered a
line pressure of 6.3 kg/cm2 (90 psi) with 3.2 kg/cm2 (45 psi) to the
sprinklers. Sprinklers on 1.5m (5 ft.) risers gave uniform area-depth sludge
applications over plots (Figure 10).
FIRST YEAR APPLICATIONS
As explained in a previous section, first year trial applications were
0.6, 1.3 and 1.9 cm weekly (100, 200 and 300 mt/ha/yr series plots; 0.25,
0.5 and 0.75 in.) in one short application to duplicate plots. A third plot
in each series received an additional 1.3 cm (100W, 200W and 300W plots)
(0.5 in.) of water to wash off sludge remaining on subordinate vegetation
and to establish effects of additional water. As shown in Figure 4, there
were also plots of no treatment (controls) to test departures from normal as
well as the duplicate plots which received 1.3 cm (0.5 in.) of water only
per week.
Plots were irrigated with sludge from July 22, 1975 to December 15, 1975
applying 1.8 to 5.5 mt/ha (0.8 to 2.5 t/ac.) of solids per week. Irrigation
was terminated (Dec. 1975) due to excess rain and re-initiated May 15, 1976
at reduced rates of sludge applications.
SECOND YEAR APPLICATIONS
Commencing May 15, 1976, sludge was diluted 3-fold with water, resulting
in a solution with 1-2.3% solids. Application rates of 0.25, 0.50 and 0.75
cm (0.1, 0.2 and 0.3 in.) per week of this sludge were made to the 100, 200,
300 and W series plots. If sludge was applied each week all year, applied
solids would range from 190 to 1580 kg (420 to 1S270 Ibs.) per week or aoproxl-
mately a range of 10 to 30 mt/ha (4.5 to 13.5 t/ac.) per year.
41
-------
The series of new plots on the Everett, Wilkeson and Mashel soils also
received total sludge application in the above ranges. Four rates of sludge
were applied to duplicate plots—0.25, 0.50, 0.75 and 1.0 cm (0.1, 0.2, 0.3
and 0.4 in.). The plots were identified as the 10, 20, 30 and 40 series
plots. Plots established on the Wilkeson and Mashel soil series are remote
from electrical power. Diluted sludge was transported to Wilkeson and Mashel
plots by a 2 1/2-ton, 6-wheel drive truck carrying a 7600-liter (2000-gal.)
tank. Sludge was gravity fed into a Deming open impeller pump powered by a
15-hp Wisconsin gas engine. The Deming pump delivers approximately 380 liters
(100 gal.) per minute at a line pressure of 6.3 kg/cm2 (90 psi). Travel time
between sites was approximately 20 minutes with 7600 liters (2000 gal.)
applied over 0.16 ha (0.4 ac.) in approximately 40 minutes.
42
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Section 14
RESULTS OF SLUDGE APPLICATIONS ON SOILS AND SOIL WATER
The following sections summarize the results of sludge applications on
soils over time by describing changes in soil properties, soil water ions
and related impacts. The forest soil provides renovation of suspended and
dissolved constituents in soils through physical filtration and chemical
reactions. The soil solution as sampled by the lysimeter plates estimates
dissolved constituents intransient in the forest soil. The transient soil
solution; provides the mechanism for transfer of both suspended and dissolved
materials from soil solution to ground water. The general term "flux" is
used to indicate the transient condition of nutrients in soil or ground
water.
Discussion of significant effects of sludge application on soil or soil
water chemicals infers a statistically significant difference at the 95%
confidence interval. An asterisk is used in the tables to indicate a signi-
ficant departure in average values. Frequently, a trend in change is
indicated. The interaction between limited numbers of samples and large
variation in forest soils restricts a rigid interpretation of statistical
significance. If additional degrees of freedom were available in sampling,
statistically significant differences would be observed. The following
sections first summarize the physical renovation of solids by the soil pro-
file, followed by sections which summarize soil solution chemicals and soil
properties. The Everett soils were studied over three years. Results are
presented as a summary of the first and second years on Everett soils and
the end impact of three years of sludge application. Only one year of data
through one growing season is available for the Mashel and Wilkeson soils.
RENOVATION OF SOLIDS
Forest soils are a very efficient physical filter of the solids normally
occurring in applied sludge. The Maz-o-rator ground most non-organic solids
sufficiently fine so they were not apparent on plots. Large first year
applications of sludge, as previously discussed, did impede infiltration
causing ponding in low spots and depressions. Even these Tow spots eventu-
ally drained with a retention of the solids on the soil surface.
Slight penetration of solids into soils was indicated in places by a
change in color of surface soils., particularly on plots which received water
following sludge applications. Penetration was only a few millimeters;
thus, the forest soil also effectively filtered for the usual 'size of organic
solids in the sludge applied. Reduced rates (second year) of sludge
43
-------
application did not cause reduced infiltration. In fact, plots with lowest
quantities of sludge application do not look significantly different from
control plots.
Total quantities of sludge actually applied to plots by years are sum-
marized in Table 2. Table 2 shows total quantities of sludge applied to
older plots on Everett soils. Heavy first year application ranged in depth
from 12.1 to 26.7 cm (4.7 to 10.5 in.). Equivalent weights of solids
applied ranged from 38.7 to 85.4 mt/ha/yr (17.2 to 38 t/ac/yr.}. Applica-
tions of sludge were continued during the first year until obvious signs of
impaired infiltration were observed. Discontinuing sludge applications at
varying times resulted in different quantities of sludge applied to individual
plots, but in no case did' the quantities applied approach design rates.
The second year of sludge application proceeded at reduced rates. Sludge
was actually applied for only 10 months; thus, maximum rates again were only
approached. Depth ranged from 0.8 to 5.3 cm (0.3 to 2.1 in.) with equivalent
weights of 2.6 to 17 mt/ha/yr (1.2 to 7.6 t/ac/yr.).
In the final year, emphasis was placed on application of sludge to new
plots on the Everett, Wilkeson and Mashel soils. Again, early termination of
sludge application did not .allow sludge to be applied at design annual rates.
However, in most cases, weekly application rates for much of the year were at
design rates; only early termination of sludge applications resulted in
reduced total amounts. Heaviest third year applications were made on Everett
soils with reduced applications on Wilkeson soils. Maximum total amounts of
sludge were applied to the older plots on Everett soils with a range of 45.1
to 108.4 mt/ha (20.1 to 48.3 t/ac.) over the life of the study. In depth,
this is a range from 14 to 33 cm ('5.5 to 13 in.).
Older plots on Everett soils as well as all new plots were excellent
physical filters of suspended organic solids common in sludge. An absolute
distinction has not been made between organic solids from sludge and larger
organic molecules identified in the total organic carbon analyses. Leaching
organic carbons deeper in soils is assumed to be as secondary decomposition
products of bio-degradable materials, as compared with organic materials
common in sludge in their original form. Thus, forest soils may be con-
sidered a 100% effective physical renovator for total suspended solids from
sludge. Flux of nutrients and colloidal organic molecules through the soil
profile must take place, in part, in dissolved forms and, in part, from
accelerated decomposition of naturally occurring organic carbon to colloid
size.
44
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Table 2. TONS OF SLUDGE APPLIED BY PLOTS AND SOILS AND
YEAR IN DEPTH AND TOTAL WEIGHTS
Plot
Everett Soil
100
100W
200
200W
300
300W
10
20
30
40
Wi Ikes on Soil
10
20
30
40
Mashel Soil
10
20
30
40
First Year Second Year Third Year
Depth Tons/ Depth Tons/ Depth
(cm) ha (cm) ha (cm)
13.3 42.6 0.8 2.6 1.2
12.1 38.7 0.8 2.6 1.2
26.7 83.2 2.5 8.0 1.4
23.5 75.2 2.3 7.4 1.3
26.0 85.4 5.3 U.O 1.9
21.6 69.1 5.3 17.0 1.5
2.0
6.2
8.2
9.3
1.5
3.1
4.4
5.8
1.5
3.3
4.8
6.5
Tons/
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3.8
3.8
-4.5
4.2
6.1
4.8
6.4
19.8
26.2
29.8
4.8
9.9
14.1
18.6
4.8
10.6
15.4
20.8
Total
Depth
(cm)
15.3
14.1
30.6
27.1
33.2
28.4
2.0
6.2
8.2
9.3
1.5
3.1
4.4
5.8
1.5
3.3
4.8
6.5
Tons/
ha
49.0
45.1
95.7
86.7
108.4
90.9
6.4
19.8
26.2
29.8
4.8
9.9
14.1
18.6
4.8
10.6
15,4
20.8
45
-------
Section 15
EVERETT SOILS, SOIL SOLUTION NUTRIENTS
Those treatments shown in Table 2 which received 1.3 cm (0.5 in.) of
water following sludge application also received quantities of dissolved
nutrients in the water, as listed on the bottom of Table 6 (kg/ha). The
amounts are insignificant by comparison with the quantities of nutrients
applied in the sludge.
Table 3 summarizes the first year nutrient loading applied in sludge and
the flux of soil solution to deeper than 2.1 m (7 ft.) in the soil profile.
Nutrients applied as a loading in the sludge (Table 3) are calculated from
average concentrations (Table 1). Flux of nutrients past the 2.1 m (7 ft.)
depths incorporates large variability in both volumes of soil solution leach-
ate (as collected by lysimeters) and concentrations of nutrients in soil
solution samples. Large concentrations of nutrients in the soil solution
coincoide with low soil moisture and very slow rates of moisture flow. Con-
versely, low nutrient concentrations in soil solutions occur during wet
conditions with large amounts of rapid flow of soil water through the soil
profile.
The renovation capacity of the soil is expressed as the percentage of
an element applied and the quantity leaching (flux) deeper than 2.1m (7 ft.)
in the soil. A large percentage renovation (Total-P, 99+%, Table 3) indi-
cates retention in the soil profile, w'ith very little leaching or flux.
Conversely, a large flux or high leaching losses indicates reduced renovation.
Renovation of the Everett soil for total nitrogen was surprisingly efficient
in view of the large quantities of total -N applied in sludge—1928 to 4261
kg/ha (1720 to 3801 lbs./ac.). The total -N flux or quantity leaching past
the 2.1 m (7 ft.) depth in the soil profile was both largest and least of
all treatments for the 300 and 300W treatments—221 to 2333 kg/ha (197 to
2081 lbs./ac.), respectively. Renovation of total -N also had a maximum
range from 32% (300W) to 95% on the 300 plots. The 200 series plots reversed
the impacts of water on the 300 plots with the 200W renovating 91% (340 kg/
ha flux or 303 Ibs./ac.) as compared to 65% (1500 kg/ha flux or 1338 Ibs./
ac.) for the 200 plot.
To date, there is no explanation for the reversal of renovation of
total nitrogen between the 200 and 300 series plots with or without water.
Great care was taken in obtaining these results with very careful checking
for errors. Clues are not offered by the 100 series plots, as the renovation
of the water added plot is not significantly different from the plot without
water. The pattern established in the first year continued in future years,
46
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and the reversal between the 200 and 300 series plots was consistent for other
elements (Ca and Mg). It can only be assumed that the differences represent
random variation in soils and their renovation abilities.
This random variation in renovation capacity also shows in the Nlty-N
differences with the 100 plot without water having significantly greater
losses (290 kg/ha or 259 Ibs/ac.) than any other plots. Losses of NH4-N were
insignificant on all other plots (1 to 29 kg/ha or 0.9 to 25.9 Ibs/ac.).
Renovation of Nfy-N ranged from 77 to 99% (290 to 1 kg/ha or 259 to 0.9
Ibs/ac.) with best renovation on those plots which received maximum amounts of
NH4-N.
The obvious and expected losses of nitrogen from plots occurred in the
N03-N form. Leaching losses ranged from 220 to 2211 kg/ha (196 to 1972 Ibs/
ac.). Again, both of these values occurred on the 300 series plots.
Again, the reversal of nitrate leaching with additions of water on the
200 series plots occurred. Almost 5 times as much nitrate was leached through
2.1 m (7 ft.) of the soil profile on the 200 plot without water application.
Differences on the 100 plots are probably not significant. Quantities of
nitrate applied to the plots are relatively insignificant in comparison to the
total quantity of nitrogen applied. The dynamics of plot chemistry are
exhibited by the rapid changes in form of nitrogen and the large leaching
losses in the soil solution as nitrate.
The renovation capacity exhibited by the Everett soil for total P, P04-P,
calcium, magnesium, sodium and potassium is excellent even in spite of the
very large quantities applied. Renovation of phosphate was 99+% with a maxi-
mum leaching loss of 2 kg/ha (1.8 lb/ac.). Applications of calcium in sludge
ranged from 31,000 to over 70,000 kg/ha (27,660 to over 62,450 Ibs/ac.).
Leaching losses ranged from 231 to 2594 kg/ha (207 to 2314 Ibs/ac.); however,
renovation was excellent in view of the very large quantities applied. Very
similar trends were exhibited for the other base nutrients with almost
insignificant leaching losses.
The greatly reduced rates of sludge application and quantities applied
(Table 2) and dilution of sludge with water resulted in significantly reduced
applications of nutrients during the second year (Table 4).
Large first year applications of sludge to the Everett soils initiated
leaching losses in the soil solution through 2.1 m (7 ft.) of the soil profile
which continued in ensuing years, maintaining similar patterns. Greatly
reduced rates of weekly nutrient applications and reduced total loadings
reduced but did not stem leaching losses. The percent renovation, in general,
was less—not because of increased losses but in calculating percentages, the
greatly reduced amounts of nutrients applied cause even a reduced flux to
show generally a lesser percentage of renovation.
Total nitrogen losses (flux) for the 100 series plots were approximately
one-half of the losses sustained during the first year (800 kg/ha, YR 1, to
48
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sustained the continued high rate of total nitrogen loss initiated in YR 1
(1784 kg/ha or 1592 lbs/ac.). Plot 200W increased from 340 to 930 kg/ha
(303 to 830 lbs/ac.). Plot 300 increased from 221 to 785 kg/ha (197 to 700
lbs/ac.) in the second year.
Again, NH^-N losses were insignificant and nitrate leaching generally
declineds particularly on the 300W plot, from an average of 2211 to 667 kg/ha
(1973 to 595 Ibs/ac.) in the second year. In the first year, nitrate leach-
ing was the major form of loss of total nitrogen from the soils. However, in
the second year substantial losses of nitrogen took place in other forms (as
yet unidentified). Losses of total phosphate and P04-P continued to be insig-
nigifcant. Leaching of calcium generally declined on all plots except for
plot 200 which showed a slight increase over first year leaching losses. The
very high leaching loss on plot 300W, 2594 kg/ha (2314 lbs/ac.), reduced to
584 kg/ha (521 lbs/ac.) in the second year. Leaching losses of other
nutrients were not significantly different in the first and second years. The
reduced rates of application make even reduced rates of leaching a lesser
value in terms of renovation.
Applications of sludge to the Everett soil plots in the third year con-
tinued at reduced rates (comparing plot averages of Tables 4 and 5). With the
exception of plot 100, total nitrogen leaching generally declined signifi-
cantly in the third year. The decline in total -N flux generally results
from reduced nitrate leaching with the average for the 100 series reducing
from 380 to 290 kg/ha (338 to 259 Ibs/ac.). The 200 series reduced from an
average of both plots of 1120 to 690 kg/ha (999 to 616 Ibs/ac.), and the 300
series reduced from 650 to 470 kg/ha (580 to 419 Ibs/ac.: Table 5).
Losses of total P and P04-P continued to be insignificant. Changes in
losses of other base nutrients are probably not significantly different during
year 3 as compared to year 2. In general, there either are no significant
differences or slight declines in leaching losses.
The total of nutrients applied in three years of sludge application and
total nutrient losses are summarized in Table 6. The most significant losses
from the soil profile are the nitrate form of nitrogen. Of the 4743 kg/ha
(4233 Ibs/ac.),of total nitrogen lost from the 200 plot, 4041 kg/ha (3605 Ibs/
ac.)—85%—were in the nitrate -N form. Losses of NH^-N are insignificant by
comparison. Retention of phosphate in the soil profile is excellent in all
of its forms with losses at background levels.
Large quantities of dissolved base nutrients in Metro sludge provide a
very significant loading when compared to the total quantities of suspended
organic solids applied. For example, the 200 series plots average 115,120
kg/ha (102,202 Ibs/ac.) of combined calcium, magnesium, sodium and potassium
in comparison with an average of 91,200 kg/ha (81,168 lbs/ac.) of suspended
solids (Table 2). Slightly greater quantities, 122,910 kg/ha (109,033 Ibs/
ac.) were applied to the 300 series plots. Suspended solids in sludge
averaged 99,650 kg/ha (88,399 Ibs/ac.) for the 300 series plots. Leaching
50
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losses of dissolved constituents are almost insignificant by comparison to
the quantities applied. With the exception of nitrogen compounds, total
renovation ot>the Everett soil ranges from 95 to 99%.
53
-------
Section 16
PROPERTIES OF EVERETT SOILS
Total chemical analyses of the Everett soil profile prior to sludge
treatments identified the quantities of base nutrients per hectare. A balance
sheet is presented in Table 7 where initial average total quantities of
nutrients are compared with total quantities applied in sludge and nutrient
flux through the soil profile. Post treatment soil chemistry would indicate
accumulations of nutrients in the soil profile. In general, total amounts of
nutrients show an increase following three years of sludge application; how-
ever, high statistical variation in Everett soils does not allow an exact
balancing of the initial quantities of nutrients. This is particularly true
with very high application rates of calcium added in the 200 and 300 series
plots. Additional quantities of total calcium applied in sludge almost
equalled the quantities determined in the forest soil (96.0 mt/ha, 43 t/ac. in
pretreatment; 81.2 mt/ha, 36 t/ac. applied for the 300 plots).
The total nutrient flux through 60 cm (24 in.) of the Everett soils is
shown as a percentage flux in Table 7. Highest percentage of base nutrient
losses occurred with maximum calcium applications for the 300 series plots
(2.2%). All other base nutrients—magnesium, sodium and potassium—had losses
ranging from an insignificant amount to 0.8% (magnesium at the 2100 level
treatments). Renovation over three years for quantities of nutrients applied
is good. Percentages are even more significant when calculated on total
quantities of base nutrients in soil profiles.
Attempts to accurately account for initial quantities of base nutrients
in the soil profile plus the quantities added by applied sludge achieved mod-
erate success. For example, for the 100 series plots an average of 96 mt/ha
(43 t/ac) of calcium existed in the surface 60 cm (24 in.) of the soil; 38.7
mt/ha (17 t/ac) were applied by sludge with a loss of 1.2 mt/ha (0.5 t/ac).
Post treatment soil sampling calculated 121 mt/ha (54 t/ac) of total calcium.
This is 12 mt/ha (5 t/ac) less than predicted by balancing input and outputs
of calcium. It is, however, within the confidence limits for calcium deter-r
minations in soils which average + 25%. Calcium estimations in the 200 and
300 series plots for post treatment quantities are much lower (110.8 and 126.1
mt/ha; 49 and 56 t/ac), when a predicted quantity should be about 175 mt/ha
(78 t/ac).
Results for magnesium were somewhat similar to the calcium results. The
quantity of 70.8 mt/ha (32 t/ac) of magnesium is predicted for the 100 series
plots. The 69.8 mt/ha (31 t/ac) calculated from post treatment soil sampling
is amazingly close. In fact, less post treatment magnesium was found than
54
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Table 7. TOTAL NUTRIENT BALANCE FOR PRE- AND POST
SLUDGE APPLICATIONS AND TOTAL PERCENT
FLUX ON THE EVERETT SOIL
Plots
100 Pre
Applied
Flux
Post
% Flux
200 Pre
Applied
Flux
Post
% Flux
300 Pre
. Applied
Flux
Post
% Flux
Ca
96.0
38.7
1.2
121.0
1.0
96.0
76.1
2.4
110.8
2.1
96.0
81.2
2.7
126.1
2.2
Mg
(metric tons
62.7
8.1
0.2
69.8
0.3
62.7
15.9
0.4
56.9
0.8
62.7
17.0
0.6
83.4
0.7
Na
per hectares)
251.5
7.5
0.1
290.3
T
251.5
14.7
0.2
167.9
0.1
251.5
15.7
0.2
296.0
0.1
K
71.2
4.3
0.1
65/1
0.2
71.2
8.4
0.1
52.8
T
71.2
8.9
0.2
82.3
0.3
55
-------
predicted, except the 300 series plots balance very well (83.4 mt/ha, 37 t/ac.
found compared to 79.7 mt/ha, 36 t/ac.' predicted).
Quantities of sodium found in post treatment plots exceeded the predic-
tion for the 100 and 300 series and were significantly low for the 200 series
plots. Total sodium was 290 mt/ha (129 t/ac.) following sludge application
where only 259 mt/ha (115 t/ac.) are predicted. The 300 series plots had
296 mt/ha (132 t/ac.) following sludge applications, where 267 mt/ha (119
t/ac.) are predicted. The 200 series plots have almost 100 mt/ha (45 t/ac.)
less than predicted. The variability in the sodium results are somewhat
expected due to the very high variability in sodium concentrations in the soil
plots. Quantities of sodium on the exchange capacity frequently had + 100%
variation.
Potassium following sludge application was close to predicted quantities
for the 300 series plots (80 mt/ha, 36 t/ac. predicted; 82.3 mt/ha, 37 t/ac.
found). Both pre- and post treatment potassium levels were highly variable
in the surface soils. Confidence limits ranged to 5 times the average
quantities in pretreatments reducing to + 50% in post treatment sampling. Low
estimation on 100 and 200 series plots may be attributed to natural variations.
Coarse alluvial soils are generally recognized as being highly variable
in physical structure, .texture, and chemical composition. The magnitude of
the variability problem is amplified when large amounts of the soil matrix
are larger than 2 mm (0.08 in.). Estimation of bulk density and accurate
identification of the active soil fraction complicate the problems of estima-
tion of a total base nutrient balance for pre- and post sludge applications.
EVERETT SOIL CHEMISTRY, FIRST AND SECOND YEARS
Detailed resampling of original plots for total chemistry for pre- and
post treatment results of base nutrients is summarized in Table 7. The 2.1 m
(7 ft.) depths were not resampled due to the extensive disturbance excavation
to this depth would have caused to the surface of plots. Pretreatment soil
analyses established average quantities of nutrient reserves in the soil.
Quantities of nutrients applied in sludge should indicate the current, total
less plant uptake and flux.
Preliminary data compared pretreatment average analyses to post treat-
ment averages for original Everett plots receiving sludge (Table 8).
Confidence interval of the mean at a 95% confidence level is calculated on
the statistics for either the pre- or post treatment, using maximum vari-
ability. The limited numbers of soil samples do not allow strict statistical
analysis but are offered only as a relative comparison of variability of soil
chemistry.
Applications of sludge during the first and second-years have increased
the variability for most soil properties analyses, as summarized in Table 8.
Random sampling of plots prior to sludge treatment developed averages for pH,
organic matter, total nitrogen and cation exchange capacity. These averages
were determined for the forest litter layers (L), the surface soils termed
the soil A horizons, and averages for soil B horizons, the 15 to 60 cm (5.9
56
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Table 8. SOIL CHEMICAL PROPERTIES FOLLOWING SLUDGE
APPLICATIONS ON THE EVERETT SOIL SERIES
AND 95% CONFIDENCE INTERVAL, SECOND YEAR
pH
Organic
Matter
(percent)
Total
Nitrogen
(percent)
Cation Exchange
Capacity
(meq/lOOg O.D. wt)
Carbon: Nitrogen
(ratio)
Horizon
L
A
B
L
A
. B
L
A
B
L
A
B
L
A
B
Pretreatment
•5.6 + 0.1
5.9 + 0.6
5.9 + 0.5
38.1 + 2.3
11.3 + 0,6
3.4 + 0.2
0.61 + 0.04
0.27 + 0.02
0.11 + 0.01
50.9 + 2.5
28.0 + 1.0
15.2 + 0.6
36:1
24:1
18:1
Post Treatment
4.8 +
5.0 +
5.3 +
32.6 +
16.4 +
4.3 +
0.82 +
0.29 +
0.09 +
59.9 +
43.5 +
18.4 +
23:1
33:1
28:1
0.9
1.0
0.8
11.6
6.5
2.0
0.31
0.15
0.06
11.3
7.2*
6.6
*Significant difference
57
-------
to 24 in.) depths. In general, the confidence limits are significantly less
for pretreatment than post treatment data. For example, a confidence limit
of + 0.1 pH unit was found in the pretreatment analyses for the forest litter
layers (L). This has increased 9-fold to 0.9 pH units for the posst treatment
soil chemical analyses.
Organic matter in the litter layer has an increased variability from
+ 2 3% to + 11.6*. Increased variability induced by sludge treatments results
from variations in sludge application rates to plots. Initial analysis of
sampling attempted to establish soil property differences between plots with
different rates of sludge application; however, inherent variability of soils
was much too great. Thus, soils from all sludge treated plots are analyzed
independent of rates of sludge application. The only significant change in
soil chemistry is an increase in average cation exchange capacity of soil A
horizons, increasing from 28.0 to 43.5 mi Hi-equivalents per 100 grams of
oven dry soil (meq/lOOg O.D.), following two years of sludge application.
The following sections discuss briefly trends found in soil chemistry.
Soil pH
Soil pH is the negative logarithm of the hydrogen ion concentration.
Soil pH values were converted to actual hydrogen ion concentrations for com-
parisons of increased acidity. Hydrogen ion concentrations increased from 26
to over 6000%. Increases in hydrogen ion concentrations are reported as a
decrease in soil pH. Average soil pH decreased for the litter layers from
5 6 to 4.8. The large variation associated with post treatment analyses will
not allow establishment as a significant difference (range 3.9 to 5.7).
Assessment of only pretreatment results suggests there has been a real reduc-
tion in average pH of the forest litter layers due to sludge application.
Additional soil sampling would be required to be sure of a statistically
significant difference.
Soil Organic Matter
Average soil organic matter tends to decrease with sludge application in
litter layers (38.1 to 32.6%) and increase slightly in the soil horizons
(11.3 to 16.4%). Patterns of variability are similar in organic matter
analyses as with pH determinations. There is a 5-fold increase in variability
of organic material content of forest litter analyses and a 10-fold increase
in variability of soil organic matter analyses in A and deeper horizons,
following sludge treatments. Based on only the determination of pretreatment
condition, we would suggest that there has been significant decreases in
organic matter of the L layer and increases in organic matter in the soil.
However, the high variability of the post treatment results does not allow
statistically significant conclusions. The trends, however, are apparent and
are supported by total organic carbon analyses and a theory of translocation
of organic colloids deeper into the soil profile.
Using these average organic matter values, pretreatment soiI analyses
indicated an average of 123.7 rat/ha- (55.2 t/ac.) of organic material (range
58
-------
72.6 to 176 mt/ha or 32.4 to 78.8 t/ac.). Post treatment analyses show an
average of 169 mt/ha (75.2 t/ac.) with a range of 96.6 to 318 mt/ha (43.1
to 142.0 t/ac.) for sludge treated plots.
Total Nitrogen
Percentages of total nitrogen tend to increase in the L layer (0.61 to
0.82$) and remain unchanged in soil horizons. Reductions in soil organic
matter in the L layer suggest there should be a reduction in quantity of
nitrogen also. Increases in organic matter in the surface soils (A horizon)
suggest there should be an increase in the quantity of nitrogen in surface
soils.
Cation Exchange Capacity
Cation exchange capacity of the A horizon of sludge treated plots is the
only soil property to show a statistically significant (P<.05) change (28.0
to 43.5 meq/100 g O.D. soil). Increases are suggested for L and B horizons
(L 50.9 to 59.9; B 15.2 to 18.4 meq/lOOg O.D. soil) with greatly increased
variation since sludge application. A mineralogic analysis revealed no
change in the type or quantity of clay minerals present in the surface soil
layers; thus, changes in total exchangeable cations must be attributed to
increases and/or the form of organic colloids.
Carbon-Nitrogen Ratio
The carbon-nitrogen ratio for pretreatment conditions on the Everett
soils is about average for forest soils. Forest litter is relatively
undecomposed; therefore, high in carbon. Advancing decomposition takes place
with incorporation in the soil profile. Changes in the carbon-nitrogen ratio
induced by sludge application reflect mainly a very significant increase in
the quantities of total nitrogen in forest litter layers. Quantities of
carbon in the organic matter layer have declined slightly; however, the
significant reduction in the carbon-nitrogen ratio is explained by increased
total nitrogen. Organic carbon is increasing in the soil profile in both A
and B horizons without equivalent increases in total nitrogen content. The
carbon-nitrogen ratio has increased in both the A and B soil horizons.
EVERETT SOILS, EXCHANGEABLE CHEMISTRY AND BASE SATURATION, SECOND YEAR
Applications of sludge over two years have significantly altered several
exchangeable cation relationships (Table 9). With the exception of sodium,
there is a general decline in the exchangeable cations in L layers. Calcium
has reduced significantly from 12.8 to 9.8 meq/lOOg O.D. Potassium has also
reduced significantly from 0.6 to 0.2 meq/lOOg O.D. while sodium has increased
from 0.1 to 0.4 meq/lOOg O.D. Magnesium shows a general trend of decline in
soil horizons with a significant reduction in the B horizon (0.8 to 0.4 meq/
lOOg O.D.). Potassium indicates a significant decline in both the A and B
horizons.
The sum of total exchangeable cations tends to decrease in the L layers
exclusive of the hydrogen ion (14.9 to 11.7 meq/lOOg O.D.). Thus, a decrease
59
-------
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in exchangeable cations accompanied by an increase in cation exchange capacity
effectively reduces the base saturation. Changes .in the quantities of
exchangeable cations in soil horizons are relatively insignificant; however,
again the large increase in cation exchange capacity, particularly of the A
horizon, results in an effective decrease in percentage of base saturation.
EVERETT SOIL CHEMISTRY, THIRD YEAR
Third year resampling of the original 100, 200, 300 series plots sampled
litter layers and the A and B soil horizons (15 to 60 cm or 6 to 24 in.).
Post treatment soil properties following three years of sludge application
are again compared with the pretreatment samples. The sampling scheme
attempted to establish the depth within the soil column where significant
changes in soil properties might be taking place. Had significant differ-
ences been found in soil B horizons, then deeper soil horizons would have
been sampled. Few significant changes in soil chemistry deeper than the B
horizon were found. Table 10 compares soil chemical properties following
three years of sludge application.
Soil pH
The pH of soil litter layers continues to decline with additional sludge
applications. pH is now significantly lower than the pretreatment pH (5.6
compared to 4.3). pH of the third year is not significantly lower than the
second year due to the high variability in second year pH results. Soil A
horizons have also declined significantly from the pretreatment (5.9 to 4.7).
pH of soil B horizon averages lower but is not significantly different from
either pretreatment or second year results. (Compare Table 10 with Table 8.)
Organi c Matter
Forest litter layers (L) show no significant changes in organic matter.
The trend of apparent decrease in the second year has been reversed in the
third year. Values for the three sampling times show normal variation. A
significant increase in the organic matter content of the soil A horizon has
taken place, while the average percentage organic matter is less (15.2%) in
the third year than in the second (16.4%). The significant increase is
established by reduced variability in the random process of sampling the
soils. The confidence limits for the third year were ± 1% as compared to ±6%
for the second year samples. These data would suggest that a significant
increase actually took place in the organic matter content with two years of
sludge application, but it was obscured by the inherent random variation.
Organic matter content of soil B horizons exhibits normal variation with no
significant differences.
Total Nitrogen
Total nitrogen concentration in forest litter layers has also increased
significantly over the pretreatment condition (0.61 to .78%). The third
year of treatment appears to have allowed soil nitrogen to also increase in
concentration in soil A horizons (0.27 to .42%). Neither of these increases
61
-------
Table 10. SOIL CHEMICAL PROPERTIES FOLLOWING SLUDGE
APPLICATIONS ON THE EVERETT SOIL SERIES
AND 95% CONFIDENCE INTERVAL, THIRD YEAR
pH
Organic
Matter
(percent)
Total
Nitrogen
(percent)
Cation Exchange
Capacity
(meq/lOOg O.D. wt)
Carbon: Nitrogen
(ratio)
Horizon
L
A
B
L
A
B
L
A
B
L
A
B
L
A
B
Pretreatment
5.6 + 0.1
5.9 + 0.6
5.9 + 0.5
38.1 +• 2.3.
11.3 + 0.6
3.4 + 0.2
0.61 + 0.04
0.27 + 0.02
0.11 + 0.01
50.9 + 2.5
28.0 + 1.0
15.2 + 0.6
36:1
24:1
18:1
Post Treatment
4.3 + 0.04*
4,7 + 0.2*
5.5 +0.3
41.2 + 3.9
1,5.2 +> 1,0*
3.1 + 0,5
0..78 +• 0.10*
0,42 +• 0.07*
0,)1 + 0.02
61.5 j^ 5.0*
43.0 + 4.0*
17.4 + 1.7 .
30:1
21 :1
16:1
*Significant difference
62
-------
are significantly different from the second year values. There have been no
significant changes in the soil B horizons.
Cation Exchange Capacity
Soil cation exchange capacity has significantly increased in both the L
layers and the soil A horizon (L, 50.9 to 61.5 meq/100 g O.D.; and A, 28 to
43 meq/lOOg O.D.). Increases in cation exchange capacity are attributed to
the increased organic matter content of the L layer and the A horizon.
Carbon-Nitrogen Ratio
The carbon-nitrogen ratio is a function of both changes in organic matter
content and changes in the total nitrogen percent. In the second year,
highly variable litter layers were sampled with a reduced organic matter con-
tent. Total nitrogen content was even higher (0.82%) than in the third year
(0.78%). This combination gave a greatly reduced carbon-nitrogen ratio in
the litter layers in the second year (23:1; Table 8). Increased organic
matter in the third year, along with a stable nitrogen content, results in an
increase in the carbon-nitrogen ratio of the litter layer (30:1). The combi-
nation of a significant increase in total nitrogen in the A horizon with a
slight decrease in organic matter results in a drastic reduction in the
carbon-nitrogen ratio over the second year (33:1 to 21:1), In a like manner,
the slight increase in nitrogen content of the B horizon accompanied by a
reduction in organic matter results in a significantly lower carbon-nitrogen
ratio (28:1 to 16:1) in the third .year of the study. While significant
changes nave taken place between the second and third years, the carbon-
nitrogen ratios currently are not significantly different from the pretreat-
ment values.
EVERETT SOILS, EXCHANGEABLE CHEMISTRY AND BASE SATURATION, THIRD YEAR
The reduction in soil pH accompanied by an increase in organic matter
and an increase in cation exchange capacity is generally reflected in a
changing composition of exchangeable cations in the third year of sludge
applications (Table 11). The initial decline of exchangeable calcium in L
layers has stabilized at a slightly lower but not significantly decreased
level. Increased amounts of calcium are becoming associated with the exchange
capacity in the A horizon. In the third year of the study, exchangeable
calcium almost doubled, resulting in a significant increase over pretreatment
amounts. A trend to increase in calcium also occurs in the soil B horizon.
Exchangeable magnesium in the soil B horizon continues to decline
.accompanied by a nonsignificant increase in the A horizon. Exchangeable
potassium increased significantly between the"second and third years in the
L layer and soil A horizon. Current values, however, are not significantly
different from pretreatment values. ;
Exchangeable sodium continues to be significantly greater with both the
L layer and A horizon showing an increase over pretreatment values. Increases
are not significantly greater from the third year over the second.
63
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The accumulation of exchangeable cations tn the sot! A horizon has
resulted in a significant increase in the percent-base saturation between
second and third year results. There are no significant changes between pre-
and post treatment data or other horizons between the second and third years.
EVERETT SOILS, REDUCED SLUDGE APPLICATIONS
Application of sludge to the new plot series at reduced rates resulted
in very similar nutrient flux and renovation during the first year of reduced
sludge application rates. Table 12 provides a summary by nutrients of the
quantities applied, losses and percent renovation by plots. Generally,
losses of nutrients (in kg/ha) were quantitatively least on the 10 plots
(minimum levels of sludge application) and generally greatest on the 30 and
40 plots which had increased sludge applications. Complex interactions
remain in processes affecting total nitrogen leaching. Losses of Nfy-N are
insignificant, again with rapid change of form of total nitrogen to NOs-N
where leaching losses occur in the soil solution.
Phosphorus losses again are insignificant with base nutrients closely
paralleling results for heavier applications of nutrients. Renovation ranged
from 96 to 99% with losses varying up to 613 kg/ha (547 lbs/ac.)--calcium--
on the 40 plots. Maximum concentrations of nutrients in the soil solution
occur during dry summer periods when volumes of soil solution are very low
and losses are really insignificant. Minimum concentrations of nutrients in
the soil solutions occur during the wet season and actually account for the
major portion of nutrient losses.
EVERETT SOIL CHEMISTRY, REDUCED SLUDGE
Analyses of impacts of reduced rates of sludge application for the first
year on the new Everett plots are summarized in Table 13. Again, average of
analyses of all sludge treated plots is compared with the pretreatment soils
analyses to assess significant impacts of sludge applications on soil
chemistry.
Soil pH
There was a significant decrease in the average pH (5.8 to 4.4) of the
forest litter layers following first year applications of sludge at reduced
rates. Reductions in the soil A horizon (5.3 to 4.7) were not significant,
but it may be anticipated that a significant reduction in soil A horizon pH
will take place, as a marked decline has occurred. Large variability in pre-
treatment pH of soil B horizons precludes any significant change caused by
sludge treatments.
Soil Organic Matter
The series of plots selected for application of sludge at reduced rates
had very large pretreatment variations in quantities of organic matter in
both the forest litter layers (45.9 + 17%) and the soil A horizon (17.7 ±
4.9%). No significant changes in soil organic matter have taken place in the
65
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Table 13. AVERAGE SOIL CHEMICAL PROPERTIES OF EVERETT (New Plots)
SOILS WITH REDUCED RATES OF SLUDGE APPLICATION
pH
Organic
Matter
(percent)
Total
Nitrogen
(percent)
Cation Exchange
Capacity
(meq/lOOg O.D.wt)
Carbon: Nitrogen
(ratio)
Horizon
L
A
B
L
A
B
L
A
B
L
A
B
. L
A
B
Pretreatment
5:8 +
5 .-3- +
5.6 +
45.9 +
17.7 +
1.8 +
0.66 +
0.24 +
0.05 +
42.4 +
29.2 +
15.3 +
40:1
43:1
21:1
0.6
0.2
1.3
17.0
4.9
1.3
0.43
0.04
0.03
6.4
3.0
1.3
Post Treatment
4.4 + 0.3*
4.7 + 0.7
5.8 + 0.2
42.3 + 9.0
15.9 + 5.0
2.9 ± 0.2'
0.64 + 0.36
0.29 + 0.02
0.07 + 0.01
73.1 + 8.6*
38.7 + 3.5*
15.4 + 1.3
38:1
32:1
24:1
*Significant difference
67
-------
soil surface, although there Is possibly a trend to tncrease in, the sotl B
horizon.
Total Nitrogen
Total nitrogen content may be increasing in the soil horizons but not
significantly so following one year of sludge applications. Large variation
in total nitrogen usually accompanies large variation in organic matter.
Total nitrogen variation is very similar to that of organic matter with no
significant differences in forest litter layers.
Cation Exchange Capacity
Cation exchange capacity-of L layers and surface soil (A) horizons
continues to be the soil property most significantly influenced by sludge
applications. Litter layers of sludge treated plots increased an average of
30.7 meq/lOOg O.D. (from 42.4 to 73.1 meq/lOOg O.D.). Cation exchange capa-
city of soil A horizons has increased significantly as a result of sludge
treatments; 38.7 as compared to 29.2 meq/lOOg O.D. soil. Soil B horizons
largely are unaltered to date by sludge applications.
Carbon-Nitrogen Ratio
Carbon-nitrogen ratios have not departed significantly as a result of
sludge treatments in L and B layers. The reduced organic matter with
slightly increased nitrogen has lowered the carbon-nitrogen ratio of the A
horizon following sludge treatment.
EVERETT SOILS, EXCHANGEABLE CHEMISTRY AND BASE SATURATION, REDUCED RATES
Few significant changes occurred as a result of sludge application at
reduced rates on the Everett soil (Table 14). The only statistically signi-
ficant change in exchangeable chemistry was an increase in the sodium content
of the B horizon from 0.1 to 0.3 meq/lOOg O.D. It is probably more interest-
ing to note the pretreatment values for the new Everett plots as compared to
the pretreatment values for the old Everett plots. (See Table 9 and 11). Ex-
changeable calcium is significantly higher in both the L and A horizons. In a
like manner, exchangeable magnesium is very close to being significantly greater.
Larger quantities of exchangeable cations for the particular location
of the new plots result in a base saturation percent significantly greater
than reported for the older Everett soil plots. The significant increases
in cation exchange capacity of the L and A horizons result in a significantly
reduced base saturation percentage following sludge treatments.
68
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Section 17
EVERETT SOIL SOLUTION NUTRIENTS, WATER AND CONTROL PLOTS
Quantities of nutrients applied in the water irrigation treatment over
the three years of study, and the natural flux of nutrients from a control
plot, indicate the natural levels of nutrient cycling (Table 15). The
untreated control plot lost 1.6 kg/ha (1.41 lbs./ac.) of total -N composed
predominantly of NO^-N (0.9 kg/ha or 0.8 Ib./ac.) or 56%. Nfy-N losses were
about equal (0.2 kg/ha control; 0.17 kg/ha water only—0.17 and 0.15 Ib./ac.,
respectively) on the two plots. Inputs of total N by water irrigation are
relatively small; however, irrigation with water does accelerate total nitro-
gen losses (2.87 kg/ha water—2.56 lbs./ac.; 1.6 kg/ha control--!.4 lbs./ac.).
Water applications apparently stimulate microbiological activity to the point
of greatly reducing nitrate losses (0.08 kg/ha or 0.07 Ib./ac.) on the water
only plots.
Losses of total phosphorus were accelerated through irrigation with
water.as compared with the control. However, fractions of kg/ha loss are
probably insignificant. Phosphate losses were reduced in the water only
plot.
The flux of calcium, magnesium, sodium and potassium are slightly
greater on the control plots than on the water irrigated plots. These losses
are probably within the range of normal point to point variation for the
Everett soil. In general, there is a conservation of base nutrient cations
within the soil profile for the quantities applied in the irrigation water.
70
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71
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Section 18
EVERETT SOILS—SOIL SOLUTION NUTRIENT CONCENTRATIONS
An important phase of interpretation of the impacts of sludge disposal
in the forest is nutrient concentrations transmitted to ground water. A
major portion of the renovation of nutrients should take place in surface
soil horizons, 2-3m (6-9 ft.). Measurement of the maximum and minimum con-
centrations of nutrients passing the 2.1 m (7 ft.) depth in the soil should
provide an index of maximum potential contributions of sludge application to
ground water.
A summary of the maximum and minimum concentrations of nutrients for all
sludge treatment plots on Everett soils is provided in Table 16. Interpreta-
tion of the meanings of average concentrations could be very misleading, as
they would be more an indices of the frequency of sampling rather than a true
average concentration. Minimum concentrations of nutrients in the soil
solution occur during rainy periods when high quantities of water are passing
the soil profile. In these circumstances, large volumes of water are collec-
ted by the lysimeters and may be collected at frequent intervals. Averaging.
of these data would provide an unrealistic estimation of average nutrient
concentrations.
Conversely, during very dry periods, particularly with low rates of
sludge application, the soils are very dry with low volumes of soil solution
extracted by the lysimeter plates. Frequently, field collections were made
at 2 to 3-week or longer intervals—the time period required for an extraction
of an adequate volume of soil solution for chemical analyses. These dry soil
samples yielded the highest concentrations of nutrients in the soil solution.
Samples would be relatively infrequent, even though concentration numbers
would be large.
Generally, higher concentrations of nutrients were found in the 100, 200
and 300 series plots without the additions of additional water. As per the
previous discussion, the 100W, 200W and 300W series plots with water follow-
ing sludge application provided an additional dilution factor. Potassium
values apparently deviate from this pattern.
TOTAL NITROGEN
Maximum concentrations of total N in the soil solution occurred on the
200 series plots. Both total N and NOs-N exceeded 400 mg/1. In general,
sludge applications followed by water and the reduced sludge application rates
resulted in much lower total N and NOg-N concentrations in soil solution.
72
-------
Table 16. MINIMUM-MAXIMUM CONCENTRATIONS OF NUTRIENTS IN THE
SOIL SOLUTION AT 2.1 m (7 ft.), EVERETT SOILS
Plots
100
200
300
100W
200W
300W
10
20
30
40
Control
Water
Total -N
2 -
2 -
3 -
2 -
, 2 -
T _
1 -
3 -
2 -
T -
T -
T -
299
466
223
156
144
250
50
136
103
131
13
14
N03-N
2 -
*T -
T -
1 -
2 -
T -
T -
2 _
1 -
T -
T-
T -
(mi
298
439
222
155
156
247
49
135
101
128
12
12
Ca
Hi grams per
10
20
3
3
5
25
8
10
9
6
1
1
- 270
- 328
- 278
- 148
- 171
- 236
- 45
- 127
- 81
- 178
- 24
- 19
Mg
Na.
K
liter)
1 -
3 -
1 _
1 -
2 -
3 -
3 -
1 -
1 -
2 -
j _
1 -
37
66
38
31
43
41
10
17
30
23
3
21
1
4
2
4
5
9
4
1
3
2
T
1
- 11
- 44
- 19
- 16
- 15
- 19
- 7
- 7
- 13
- 8
- 6
- 9
1 .,
1 -
1 -
1 -
1 -
2 -
1 -
4 -
2 -
4 -
1 -
T -
38
5
5
61
12
14
3
12
12
16
68
4
*Denotes less than 0.5 mg/1
73
-------
Reduced rates of sludge applications (10 to 40 plot series) resulted in
reduced total N and NOg-N in soil solutions.
BASE NUTRIENTS
Patterns of concentrations of base nutrients in the soil solution are
similar to that for total N and N03-N. Maximum concentrations of Ca, Mg and
Na occurred on the 100, 200, 300 series plots with the maximum values occur-
ring on the 200 plots. Applications of water following sludge resulted in
increased minimum values of Ca and Na for the 300W plot.
Reduced rates of sludge application with the 10, 20, 30, 40 series plots
resulted in significantly reduced concentrations of these nutrients in the
soil solution. Patterns of base nutrient occurrence in the soil solution
suggest a complex interaction between soils and applied sludge. Consistent
patterns of increasing quantities of nutrients in the soil solution with
increasing rates of sludge application are not evident for many nutrients.
Table 16 also compares maximum and minimum concentrations of nutrients
in the soil solution for the control and water only plots. Water irrigation
does not seem to accelerate nutrient losses nor contribute particularly to
excessive quantities of nitrogen or base nutrients in the soil solution.
EVERETT SOILS, SOIL SOLUTION CONDUCTIVITY, pH AND ALKALINITY
Ranges of conductivity, pH and alkalinity of soil solutions by plot
treatments and ground water are summarized in Table 17. Conductivity
(specific conductance measured in micromhos per square centimeter) of sludge
treated plots has maximum values on the 100, 200, 300 series. Minimum values
are also higher for these sludge treatments. The control plot., however, has
the maximum recorded conductivity (3427 micromhos) while both the control and
water plots have the lowest minimum values recorded. The wide range in
maximum conductivities for other plots suggests that sludge treatments are
not adding more dissolved ions to the soil solution, as treated plots do not
equal the control. There is an indication, however, that minimum values on
the average are increased with sludge treatments. Ground water tends to
buffer at a higher minimum and a lower maximum (142-194 micromhos) conduc-
tivity.
Patterns of soil solution pH are similar to nutrient concentrations and
conductivities, with the 100, 200, 300 series plots showing increased maxi-
mum and reduced minimum values (range 4.0 to 8.4). The 100W, 200W, 300W
series generally have high maximum pH values (average 7.9), but the low pH is
a whole pH unit higher than sludge only series.
The control plot has a very narrow range of pH (7.0 to 7.4) indicating
that sludge treatments are both depressing low pH values and increasing
maximum pH values. Plots with reduced rates of sludge application appear to
have lower minimum values, but on the average, maximum values have not been
increased. Ground water ranges from 7.3 to 8.1 with an average value of
7.8.
74
-------
Table 17. CONDUCTIVITY, pH, AND ALKALINITY OF THE SOIL
SOLUTION AND GROUND WATER FOR EVERETT PLOTS
Plots
100
200
300
100W
200W
300W
10
20
30
40
Water
Control
Ground Water
X
Cond.
y mhos
62 -
175 -
138 -
53 -
52 -
85 -
132 -
85 -
102 -
71 -
41 -
45 -
142 -
171
1856
2293
1536
906
970
1087
1060
1013
368
974
101
3427
194
PH
4.0
6.1
5.5
5.8
5.0
. 6.7
6.2
6.0
6.5
6.9
6.3
7.0
7.3
7
- 8.4
- 7.7
- 7.6
- 7.8
- 8.0
- 7.9
- 7.1
- 7.2
- 7.4
- 7.4
- 7.5
- 7.4
- 8.1
.8
Alka.
mg/1
0.1
0.2
0.1
0.2
0.1
0.5
0.1
0.1
0.2
0.3
0.2
0.2
1.0
1
- 8.8
- 1.0
- 0.4
- 1.0
- 2.3
- 1.0
- 0.2
- 0.3
- 0.6
- 0.5
- 0.5
- 0.7
- 1.7
.3
75
-------
Patterns of soil solution alkalinity are difficult to interpret. In
general, it appears that sludge applications have had little impact on either
maximum or minimum values. Two plots are exceptions to this statement—the
100 plot and 200W. In both cases, the maximums are significantly higher than
other values, particularly for the water or control plots (0.5 and 0.7 mg/1,
respectively).
The results of use of the Metro-data loggers for rapid scan of the con-
centration of dissolved oxygen, solution pH, conductivity and temperature
resulted in complex computer plots. Examples of these plots are shown in
figures in Appendix B.
76
-------
Section 19
EVERETT SOILS, GROUND WATER NUTRIENTS
A well drilled to the interface of the outwash gravel and lacustrine
deposits provided sampling of ground water adjacent to original Everett plot.
Dissolved chemicals of ground water are summarized in Table 18. Total N
averaged 0.8 mg/1 with a range of 0.5 to 1.4 mg/1. Other forms of nitrogen,
Nfy-N and NOs-N, averaged 0.2 and 0.4 mg/1 with no consistent relationship
between the two nitrogen forms. The maximum Nfy-N concentration was 0.7"
mg/1 while the N03-N maximum concentration was 0.6 mg/1.
Forms of phosphorus are practically nonexistent in the ground water. A
maximum of 0.18mg/1 occurred on one occasion as P04-P. Total P averaged
0.06 mg/1 and PO^P averaged 0.03 mg/1. Concentrations of base nutrients are
relatively stable in ground water showing slight seasonal variation. Anions
of S04 and Cl exhibit considerably more variation with $04 ranging from 3 to
25 mg/1, averaging 11 mg/1. The range for Cl was 1 to 45 mg/1, with an aver-
age of 11 mg/1. The range of TOC was also large—4 to 40 mg/1.
77
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78
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Section 20
MASHEL SOILS, SOIL SOLUTION NUTRIENTS
Experimental designs parallel to the Everett soil studies evaluated
impacts of sludge applications at reduced rates to Mashel and Wilkeson soils.
Design rates of application were not achieved as sludge was only applied for
7 months. Table 19 indicates the design rate (by plot number) and actual
rate of sludge applications with nutrient loading, flux (kg/ha) through the
Mashel soil, and percent renovation achieved. Patterns of flux and renova-
tion are very similar to reduced rates of sludge applications on the Everett
soil.
The characteristic wetness of the Mashel site was obvious immediately
after irrigation periods. Ponding occurred in depressions and would slowly
infiltrate over a period of days. Ponding was more noticeable after a total
15 tons of solids were applied on a plot.
The lateral movement of subsurface soil water was greater than vertical
soil water flux on sloping Mashel soils. Calculation of nutrient renovation
was more difficult without exact measurements of downward water flux.
NUTRIENT RENOVATION FOR THE MASHEL SOIL SERIES
Table 19 shows the nutrient loading, flux and percent renovation for the
four rates of sludge applications to Mashel soils. As seen with the Everett
plots, renovation of total P, P04-P, and cations Ca, Mg, Na and K is excel-
lent. Total N flux increases with increasing applications of sludge and is
again dominated by the N03-N losses.
Renovation of total N varied from 46 to 82% with increased percent
renovation on 40 treatment plots (82%). Losses of NH4-N were greatest with
the 20 and 30 series plots (39 and 59 kg/ha or 35 to 53 Ibs/ac.). Losses of
total N are dominated by NOs-N leaching (65 to 80%). Other forms of nitrogen
loss are operative though unexplained at this time, as up to 35% of total N
losses are unaccounted for by the combination of NH^-N and N03-N flux.
Excellent renovation (99+%) of phosphorus compounds continue with a
maximum of 5 kg/ha (4.5 Ibs/ac.) leached on the 30 series plots.
In a like manner, renovation of base nutrients continues to be very
efficient with 93 to 99+% of applied base nutrients retained in the surface
soil. Maximum losses occurred on the 20 and 30 series plots where total base
79
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nutrient flux was 336 kg/ha (300 Ibs/ac.) for 20 plots and 359 kg/ha (320
Ibs/ac.) for 30 plots.
81
-------
Section 21
MASHEL SOIL PROPERTIES
Usual forest soil sampling problems with large inherent natural spatial
variation in soil properties were even greater on plots on Mashel soils.
Highly variable soil chemistry of pretreatment soils analyses, particularly
soil organic matter and total nitrogen, made identification of significant
changes in soil properties due to sludge application difficult. Again, all
sludge treated plots were combined for test comparisons with pretreatment or
control conditions (Table 20). The Mashel soil is inherently more acid,
contains less organic matter, has lower average total N and cation exchange
capacity than Everett soils.
SOIL pH
Sludge applications caused no significant changes in pH of the Mashel
soil. A trend seems to indicate reduced pH in the L layer and increased pH
(4.8 to 5.2) in the B horizon at 15 to 60 cm (6 to 24 in.) of depth; however,
pre- and post treatment results broadly overlap.
SOIL ORGANIC MATTER
A nonsignificant trend to increased soil organic matter and organic
matter of L layers exists. However, as previously noted, the very high
natural variability of organic matter in the Mashel soils prevents establish-
ment of significant differences from first year sludge treatments.
TOTAL NITROGEN
A trend to reducing total nitrogen in the L layers and increasing total
nitrogen in soil horizons is suggested. Again, the highly variable results
from pretreatment total N analyses preclude establishment of significant
changes in total soil nitrogen of the Mashel soils.
CATION EXCHANGE CAPACITY
Statistically significant increases in cation exchange capacity were
found in L (14.8 to 61.9 meq/lOOg O.D.) and A (6.9 to 23.1 meq/'IOOg O.D.)
soil layers following sludge treatments. Increases in soil organic matter
may explain a portion of the increase in cation exchange capacity.
82
-------
Table 20. SOIL CHEMICAL PROPERTIES FOLLOWING SLUDGE
APPLICATIONS ON THE MASHEL SOIL SERIES
pH
Organic
Matter
(percent)
Total
Nitrogen
(percent)
Cation Exchange
Capacity
(meq/lOOg O.D. wt)
Carbon: Nitrogen
(ratio)
*
Horizon
L
A
B
L
A
B
L
A
B
L
A
B
L
A
B
Pretreatment
4.9 +
4.7 +
4.8 +
26.0 +
3.4 +
0.4 +
0.49 +
0.06 +
0.03 +
14.8 +
6.9 +
6.2 +
31:
33:
8:
0.6
0.9
1.3
27.9
8.4
1.2
0.56
0.04
0.02
8.8
3.5
6.3
1
1
1
Post Treatment
4.6 +
4.7 +
5.2 +
35.0 +
7.7 +
1.8 +
0.29 +
0.14 +
0.05 +
61.9 +
23.1 +
9.3 +
70:
32:
21:
0.4
0.3
0.5
16.1
4.3 '
0.7
0.12
0.09
0.01
15.6*'
5.1*
1.4
1
1
1*
*Significant difference
83
-------
CARBON-NITROGEN RATIO
An increase in organic matter content of the B horizon, without
equivalent increases in total N, caused a significant increase in the carbon-
nitrogen ratio (8:1 to 21:1). No significant change occurred in L or A
layers. The highly variable organic matter content of L layers combined with
equally variable amounts of total N make even the 70:1 post treatment value
an insignificant difference.
MASHEL SOILS, EXCHANGEABLE CATIONS AND BASE SATURATION
Analyses of impacts of sludge applications on exchangeable soil chemis-
try and base saturation are summarized in Table 21. Applications of sludge
have either stabilized-the large natural variability in exchangeable calcium
throughout the soil profile, or an improved random sample was obtained for
post treatment. Highly variable pretreatment Ca analyses span the range of
post treatment analyses. However, it appears that the large quantities of
dissolved Ca in Metro sludge have increased exchangeable Ca throughout the
soil. These cannot be claimed as significant increases at this time but a
trend is indicated.
A significant increase in exchangeable Mg occurred in the I, layer and
B horizon. A trend to increased Mg also is indicated in the A horizon.
There are no apparent trends in exchangeable K resulting from sludge
applications. A significant increase similar to Mg occurred with exchange-
able Na, as increased Na occurred in the L layer with a definite trend to
increase in the A horizon. Again, a smaller but significant increase
occurred deeper in the soil profile of the B horizon. The large significant
increase in exchangeable Na in the L layer (0.1 to 0.7 meq/lOOg O.D. soil)
and trend to increased base nutrients in soil horizons suggest a substantial
base nutrient leaching in the Mashel soils.
High variability in pretreatment base saturation analyses allows no
conclusion as to impacts of sludge on the Mashel soil at this time.
84
-------
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Section 22
WILKESON SOILS—SOIL SOLUTION NUTRIENTS
Similar analyses were made for interpretation of the impacts of
reduced rates of sludge application on Wilkeson soils. These results are
summarized in Tables 22, 23 and 24 which analyze nutrient loading and flux,
pre- and post treatment soil chemistry, and analysis of exchangeable base
cations.
Renovation of total nitrogen ranged from 69 to 89% (on plots 30 and 10,
respectively; table 22). Losses of NH^-N from the 30 series plots also are
large (43 kg/ha; 38 Ibs/ac.) on the Wilkeson soil. Losses of N03-N follow
usual patterns (41 to 260 kg/ha; 37 to 232 Ibs/ac.). However, a larger
percentage (80 to 99%) of total -N loss is in the N03-N form.
Usual patterns with phosphorus compounds retention prevail with insig-
nificant leaching or flux. Base nutrients—calcium, magnesium, sodium and
potassium—also exhibit usual patterns with leaching losses varying from 6%
(sodium, 44 kg/ha; 39 Ibs/ac.) to less than 1% (17 kg/ha; 15 Ibs/ac.) of
magnesium. In general, the patterns of renovation for the three soil series
tested are very similar. Maximum total flux of base nutrients (548 kg/ha;
489 Ibs/ac.) was associated with maximum sludge applications (40 plots).
WILKESON SOILS—SOIL PROPERTIES
The pre- and post treatment analyses of soil chemical properties are
summarized in Table 23.
Soil pH
The Wilkeson soil is naturally significantly more acid (pH 3.6 to 4.5)
than either the Everett (pH 5.3 to 5.8) or the Mashel (pH 4.7 to 4.9). Sludge
treatments induced a significant increase in pH on the Wilkeson soil (pH 3.6
to 5.6) in the L layers and surface soil horizons (pH 3.5 to 5.0). A trend
to increasing pH is also indicated at greater depth than the soil profile.
Soil Organic Matter
A marked trend to increased organic matter of L layers also occurred on
the Wilkeson soil (23.3 to 44.8%). A trend to increase soil organic matter
appears in the A horizon but is insignificant.
86
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87
-------
Table 23. SOIL CHEMICAL PROPERTIES FOLLOWING
SLUDGE APPLICATIONS ON THE WILKESON
SOIL SERIES AND 95% CONFIDENCE INTERVAL
PH
Organic
Matter
(percent)
Total
Nitrogen
(percent)
Cation Exchange
Capaci ty
(meq/lOOg O.D. wt)
Carbon: Nitrogen
(ratio)
Horizon
L
A
B
L
A
B
L
A
B
L
A
B
L
A
B
Pretreatment
3
3
4
23
13
1
0
0
0
20
13
3
,6 +
.5 +
.5 +
.3 +
.6 +
.3 +
.36 +
.12 +
.05 +
.3 +
.4 +
.8 +
38:1
66:1
15:1
0
0
0
16
4
0
0
0
0
14
6
4
.5
.4
.7
.7
.9
.7
.06
.08
.02
.6
.3
.1
Post Treatment
5.
5.
5.
44.
15.
1.
0.
0.
0.
77.
36.
12.
6 +
0 +
0 +
8 +
4 +
7 +
38 +
20 +
04 +
4 +
9 +
6 +
68:
45:
20:
0.
0.
0.
8.
6.
0.
0.
0.
o'.
10.
12.
0.
1*
1*
1
6*
6*
2
2
1
4
04
06
01
3*
8*
3*
*Significant difference
88
-------
Soil Nitrogen
Trends to increases in soil organic matter on the Wilkeson soil following
sludge treatment suggests a quantitative increase in total nitrogen. A sig-
nificant increase in the concentration of total nitrogen was not found. A
trend to increasing total soil nitrogen in the A horizon is indicated (0.12%
pretreatment to 0.20% post treatment). An increase in concentration of this
magnitude in the soils would yield a significant quantitative increase in
total nitrogen per hectare following sludge treatments.
Cation Exchange Capacity
Very significant increases in cation exchange capacity in all horizons
resulted from sludge treatments on the Wilkeson soil. L layers increased
from 20.3 to 77.4 meq/lOOg O.D. soil. Surface soil horizons (A) increased
from 13.4 to 36.9 meq/lOOg O.D. soil. At greater soil depths, exchange capa-
city also increased significantly averaging 12.6 meq/lOOg O.D. soil.
Carbon-Nitrogen Ratio
The carbon-nitrogen ratio of L layers significantly increased with
applications of sludge. Large increases in organic matter content of the
L layer, without an equivalent increase in total nitrogen, resulted in,a
marked increase in the quantity of carbon (38:1 to 68:1). In contrast, soil
A horizons significantly decreased in carbon-nitrogen ratio, caused by a
marked increase in total N in the A horizons without an equivalent increase
in the percentage of organic carbon (change was 66:1 to 45:1). No signifi-
cant change occurred in the carbon-nitrogen ratio of the B horizon.
WILKESON SOILS, EXCHANGEABLE CATIONS AND BASE SATURATION
The large quantity of dissolved calcium in Metro sludge again causes a
significant increase in exchangeable calcium in the L layers of the Wilkeson
soil (7.1 to 24.2 meq 100/g O.D. soil; Table 24). Average increases occur
in both A horizons and deeper soil horizons but are not significant. General
increases also occur in exchangeable magnesium throughout the soil layers but
are not of sufficient magnitude to be statistically significant. Potassium
results are more variable in the surface soil but also tend to be increasing.
Sufficient amounts of sodium have been applied in sludge and have
leached through soil profiles to add a significant amount to the cation
exchangeable complex. In the L layers, exchangeable sodium has increased
from 0.01 to 0.9 meq/lOOg O.D. soil. A horizons have increased from 0.1 to
0.5 meq/lOOg O.D. soil. The quantities of sodiumaleaching to greater depths
have also been sufficient to provide a significant increase in exchangeable
sodium in the 15 to 60 cm (6 to 24 in.) soil layers (O.Vto 0.3 meq/lOOg
O.D. soil). Impacts of sludge application on the percentage of base satura-
tion are variable and inconclusive at this time.
89
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Section 23
MASHEL AND WILKESON SOILS,
SOIL SOLUTION NUTRIENT CONCENTRATION
Concentrations of nutrients in the soil solution of Mashel and
Wilkeson soils expressed as mg/1 are summarized in Table 25. Minimum values
for total N are higher than those reported for the Everett soil; however,
maximum concentration of total N tends to be less. The flux of total N is
again dominated by N03-N losses. Concentrations of total N and N03-N are
not significantly different in the two soils. Minimum values for retention
of Ca are lower in the Mashel than the Wilkeson. Maximum values are also
higher for the Wilkeson soil. In general, the Wilkeson appears to have an
increased capacity to retain cations (Tables 21 and 24), even though all base
nutrients in the soil solution have generally increased minimum values when
compared to the Mashel soils. The significant increase in a cation exchange
capacity (Table 23) is not yet reflecting in increased quantities of cations
retained in the Wilkeson soil. There is little difference in the two soils
in maximum concentrations for Mg and Na; however, maximum and minimum concen-
trations of K are significantly greater for all treatments in the Wilkeson
soil.
91
-------
Table 25. RANGE IN NUTRIENT CONCENTRATIONS
OF THE SOIL SOLUTION BY PLOTS FOR
THE MASHEL AND WILKESON SOILS
Soils &
Plot Total -N
Mashel
10 7-55
20 11 - 55
30 5 - 124
40 5 - 127
Wi Ikes on
10 6-73
20 6-52
30 31 - 82
40 9 - 128
N03-N Ca Mg Nat K
(milligrams per liter)
7-54 10-52 4-18 5 -• 19 1-5
11 - 54 9-58 3-19 8 - 31 1-8
4 - 124 10 - 146 5-34 9 - 27 4-15
3-126 7-71 3-10 8 -• 16 1-16
6-73 23-93 6-16 17 - 29 4-18
6-52 15-74 4-13 9-18 7-23
30 - 82 34 - 105 8-18 14 - 23 13-20
8 - 128 18 - 158 6 - 31 12 - 27 16 - 39
92
-------
Section 24
EVERETT SOIL, TOTAL ORGANIC CARBON
_ Study of total organic carbon (TOC) leaching by the soil solution was
limited to plots on the Everett soils. Analyses of TOC are presented in
three phases: First, the migration of TOC in soil solution through the soil
profile, where organic constituents are not identified—only quantitatively
related to depths in the soil profile.
A second phase of analysis identifies the molecular size fractions
leached by the use of gel filtration chromatography. Identification of sizes
allows evaluation of physical filtering by the soil matrix and preliminary
indications of rate of leaching by molecular size.
_ The final analysis identifies specific organic, compounds identifying
their source. TOC analyses are confined to organic matter of colloidal size
or smaller. Soil solution samples collected from L, A, B and C horizons of
control, water only, and various sludge plots are analyzed for TOC to provide
an overview of effects of treatment on amounts of organics leaching through
I \J i co t* o O I IS*
TOTAL ORGANIC CARBON LEACHING
Leaching of TOC through soil profiles may be best summarized in a series
of figures showing quantitative amounts of TOC with depth (Fig 11 ) The
water only and control plots are compared with the 100, 200 and 300 plot
sludge treatments. A very significant increase in the quantity and depth of
leaching of TOC occurs with sludge applications. Maximum transport of TOC
through the soil profile occurred with the 200 series plots. A size fraction
is apparently transported to the C horizon in the 200 series plots, as both
the 100 and 300 series plots show a continuous decline in the quantity of TOC
through the C horizon.
The control and water only plots have much lower quantities of TOC
throughout the soil profile. Water applications have increased TOC in both
the A and B horizons.
Leaching of TOC in the 100W, 200W and 300W plots significantly departed
the patterns established with sludge only plot (Fig. 12 ). Generally, reduced
amounts of TOC occur in the litter layers, with even greater reduction in the
soil A and B horizons. Large increases are generally identified in the C
horizons with a maximum in the 300W (70 mg/1) which is nearly equivalent to
the accumulation noted on the 200 plot (Fig. 11)
93
-------
175-1
150
125
100
D)
o
L A
Figure 11.
SOIL HORIZON
Average TOC values versus depth for water,
control, and sludge treatments.
94
-------
150-1
125-
100-
D)
E
«_x
O
O
75-
50-
25-
I 1
L A
B
SOIL HORIZON
Figure 12. Average TOC versus soil depth for
the sludge followed by water sites,
95
-------
An example of changes tn TOC over time with maximum sludge applications
(300 series plot) is shown in Figure 13. Sampling is identified for the L,
A, B and C horizons. Very significant reductions in TOC in the L layers
occur with continued applications of sludge (250 mg/1 pretreatment to 20 to
40 mg/1 after 20 months of sludge applications).
Soil A and B horizons exhibit a similar early pattern of reduction in
TOC declining from 165 mg/1 in the A and 135 mg/1 in the B to less than 30
mg/1 in 20 months. Soil B horizons exhibit a somewhat inconsistent pattern
of accumulation and depletion seasonally, while C horizons show irregular
variations over time.
In general, the summer season has increased TOC with rapid decline in
the winter and increases in the following summers. Patterns of movement
were not consistent within the soil profile for equivalent times.
Gel Filtration Chromatography
Preliminary examination of the chemical nature of organic materials
responsible for TOC values in the soil solution was done by fractionating the
organic material according to molecular size using gel filtration chroma-
tography. Detection by UV spectrometry at 254 mm identifies aromatic and
other unsaturated structures.
Gel filtration chromatograms of the soil solution from several soil
horizons in the control plot and sludge plots are compared in Figure 14.
Litter samples from the control plot show a large quantity of higher molecu-
lar weight organic molecules (early peak on left), which is missing from the
sludge plots (increased late peaks). The C horizon sample from the sludge
plot contains a larger amount of low molecular weight organic materials.
Chromatograms for 1977 soil solutions are shown in Figure 15. The C
horizon of the 300 series plot shows two large peaks which are not very
evident in the C layer of the 10 series plots. These peaks tend to coincide
with natural organic material in the L layer, indicating that sludge appli-
cations over time leach organic material in the soil solution to greater
depths in the soil profile. The slight peaks in the well water coincide.
These peaks were also identified in soil solution samples from the control
plots (Figure 14, control C), indicating they are not organic contaminants
from sludge application—only natural organic compounds leaching to ground
water.
IDENTIFICATION OF SPECIFIC OR6ANICS
Soil solutions from B and C horizons of 300 series sludge plots were
composited, freeze dried, extracted with diethylether, methylated with diazo-
methane and analyzed by gas chromatography on a diethylene glycol succinate
(DECS) column. Organics could not be identified, other than phthalate
esters—a common contaminant in this system and in trace work in general. An
alternative method examined organics concentrated on soil particles.. Soil
samples were collected by horizons, extracted with moist ether and processed
-------
250-i
O)
J.
0125-
O
•LITTER
I
I
t f
B HORIZON-*/
C HORIZON—••.....
7/75
3/76
11/76
5/77
Figure 13. TOC versus date of sample collection for the
300 plot from the four soil depths.
97
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by gas chromatography. The A horizon chromatograms from the 300 series
sludge plot and control show very similar patterns (Fig. 16). After three
years of sludge application, there are no major organic inputs from sludge
detectable by gas chromatography.
In a similar manner, B horizon chromatograms are nearly identical except
for an increase in compounds labeled H, I, and J in the 300 series sludge
plots. A compound labeled X (Fig. 17) is present in small quantities on the
sludge plot and not shown in the control plot. A further check on the
organic constituents in control and sludge treated plots was tested by gas
chromatography using ether extraction and a DEXSIL 300 column. This sampling
compared gas chromatograms of ether extracts of the B horizon of the 100
series sludge plots with a similar extract from the B horizon from the con-
trol plot (Figs. 18 and 19).
Chromatograms show sludge and control plots qualitatively contain the
same organic compounds, again indicating little or no movement of ether
extractable organics from sludge through the soil profile.
Mass spectral analysis of the gas chromatograph effluents allowed the
following identification to be made:
Peak
A
B
C
D
E
F
G
H
I
J
Molecular
Wei ght
256
270
316
314
354
368
382
Identify
Unknown
Pentadecanoic acid methyl ester
Palmitic acid methyl ester
Unknown
Unknown
Isopimaric acid methyl ester
Dehydroabietic acid methyl ester
Diacosanoic acid methyl ester
Triacosanoic acid methyl ester
Lignoceric acid methyl ester
Fatty acids B, C, H, I and J have been reported previously as organic
materials found in peat and various soils (Braids and Miller, 1975).
This is the first identification of isopimarie and dehydroabietic acids
in forest soils; however, these organics are common oleoresins and undoubt-
edly form from foliage and litter decomposition.
The identified compounds are all either natural products (isopimarie,
etc.) or have been previously reported in soil; therefore, the sludge appli-
cations introduce no major new organic compounds to the system.
100
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Section 25
EVERETT SOIL, BIOLOGICAL DECOMPOSITION
Sludge applications in the forest environment potentially may alter
rates of biological decomposition of naturally occurring plant residues,
lignin and cellulose materials. Study of impacts of sludge applications on
biological decomposition rates investigated soda solubility and weight loss
of wood blocks. Results of decomposition studies are summarized by type of
analyses with trends over time in the following sections.
SODA SOLUBILITY
Soda solubility is defined by the weight loss of decaying cellulose as
extracted by a 1% sodium hydroxide solution (1% NaOH). Changes in soda solu-
bility as examined by this extraction and tested against standard samples
must be interpreted. As standard wood block samples are used as a base and
extracted weight subtracted from the test samples, a gain in weight shows as
a negative or decrease in relative soda solubility. A loss in weight shows
up as a plus or increase in soda solubility. Increases in soda solubility
represent increasing decomposition, as summarized in Figure 20 and Table 26.
Decomposition on Litter Surface
All sludge treated plots decreased ( 1 3 to 24%) rapidly in relative
soda solubility in the first 30 days (Sept. to Oct., 1975) of exposure
(Fig. 20, Table 26). Declines (.1.9 to 2.5%) in soda solubility were gener-
ally maintained in all treated plots until May 1976. An exception to this
general trend is the 100 series plots where there was an increase (12.6 to
13.7%) i;n soda solubility which occurred between October and February. This
increase was followed by a slight decline (1.2%) between February and May.
The control sample did not differ significantly in soda solubility from
the standard between October and May.
Decomposition in all plots increased significantly between May and July.
Soda solubility increased 3% for the control plots; 2,8%, 1.6% and 3.8% for
the 100, 300 and 300W plots, respectively.
Resampling a year later in July 1977 again showed significant increases
in decomposition as indexed by increased soda solubility. Different rates of
sludge application did not significantly alter decomposition rates on the
surface of the litter layers for the wood blocks. Soda soluble weight
increases were 5.3%, 7.6%, 7.9% and 6.9% for the control, 100, 300 and 300W
plots, respectively.
105
-------
f—I
CO
o
CO
o
CO
UJ
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-20-
SONDJFMAMJJA
1975 1976
J J A
1977
Figure 20. Changes in 1% NaOH solubility of wood blocks on top
of the litter over time by sludge treatments.
106
-------
Table 26. DECOMPOSITION OVER TIME ASSESSED BY SODA SOLUBILITY
EXTRACTIONS (PERCENTAGE OF DRY WEIGHT) OF WOOD BLOCKS
BY VARIOUS DEPTHS AND TREATMENTS!
Plots and
Horizons
Oct. '75
Sampling Dates
Feb . May
July '76
July '77
Control Plot
100
300
L
A
B
Plots
L
A
B
Plots
L
A
B
15
14
15
12
12
12
12
12
1.3
.7+0.
.6+1.
.3+0.
.6+0.
.1+0.
.6+0.
.8+0.
.3+0.
.5+0.
9
4
8
7
7
3
6
3
3
14.
15.
16.
13.
13.
14.
12.
11.
11.
1+0.5
5+0.2
1+0.5
7+0.2
1+0.5
4+0.3
4+0.4
1+0.3
8+0.1
15.
13.
15.
12.
12.
14.
12.
12.
12.
0+0.2
2+0.3
4+0.1
5+0.5
1+0.2
0+0.1
5+0.3
5+0.0
5+0.7
18.
14.
14.
15.
15.
16.
14.
14.
15.
0+0.5
9+0.2
3+0.2
3+0.0
5+0.1
9+0.2
1+0.2
9+0.2
5+0.0
23.3+1.7
22.3+0.4
— ~
22.9+0.3
22.7+0.0
— — —
22. 02/
24.0+0.2
— — —
300W Plots
L
A
B :
13
13
15
.7+0.
.6+0.
.3+0.
0
,2
,5
11.
11.
14.
7+0.2
7+0.2
,4+0.0
13.
13.
13.
1+0.3
1+0.5
5+0.2
16.
9+0.4
16.6+0.0
17.
0+0.0
23.8+1.3
23. Da/ '
—
\] Standard sample solubility 15.6+0.3% (September 1975)
a/ Estimated from A or B horizon samples
I/ Samples lost from B horizons for last sampling date.
107
-------
Decomposition in A Horizons
Patterns of soda solubilities in A horizons were similar for all sludge
treated plots. Decline in soda solubility (interpreted as a resistance to
decomposition) occurred for all sludge treatments between September 1975,
when the experiment was initiated, and the following May (1976).
Wood blocks in the control plot showed increased (0.9%) soda solubility
in soil A horizons between October and February, with a decline (2.3%)
between February and May. The control and all sludge treated plots showed
significant increases in decomposition between May and July. Increases were:
control, 1.7%; 100 plots, 3.4%; 300 plots, 2.4%; and 300W plots, 3.5%.
Sampling in July 1977 again revealed marked increases in decomposition.
Increased decomposition did not vary significantly between plots and was
equivalent to decomposition at the surface of the litter layer. Values were:
control, 7.4%; 100 plots, 7.2%; and 300 plots, 9.1%.
Decomposition in B Horizons
In general, patterns of decomposition in the soil B horizons were very
similar to the litter surface and A horizons. Only the 300W plot showed no
significant decline in soda solubility in the first month of exposure.
Between October and May, both the 300 and 300W plots showed a decline (13.5
to 12.5% and 15.3 to 13.5%) in soda solubility.
The 100 plots declined 3% in the first month of exposure (Sept. through
Oct.). A significant increase in soda solubility occurred between October
and February; however, no significant change took place between February and
May. Patterns of increased soda solubility for treatment plots were very
similar in A and B soil horizons. Soda solubility increased 2.9%, 100 plots;
3.0%, 300 plots; and 3.5%, 300W plots,from May to July 1976.
The control plot showed a decline (15.4 to 14.3%) in soda solubility
between May and July.
WEIGHT LOSS DECOMPOSITION
Assessment of decomposition by comparison of net weight loss with
standard wood block samples provides another index of impacts of sludge
applications on forest decomposition rates. In general, the control and
100 plots responded in a very similar fashion if weight loss is a guide to
rates of decomposition. The 300 and 300W plots also responded in a very
similar fashion; however, the response of the two sets of plots was signifi-
cantly different. Results of weight losses over time are summarized in
Table 27 and shown graphically for the litter surface in Figure 21.
Decomposition on Litter Surface
The first 30 days of exposure resulted in a weight loss of 4.6% and 3.4%
for the control and 100 plots (Table 27). In the September through October
108
-------
Table 27. DECOMPOSITION OVER TIME ASSESSED BY WEIGHT LOSS
(PERCENT OF THE DRY WEIGHT) OF WOOD BLOCKS BY
DEPTHS AND TREATMENTS
Sampling Date
Plots and
Horizons
Control Plot
L
A
B
100 Plots
L
A
B
300 Plots
L
A
B
300W Plots
L
A
B
Oct. '75
4.6
3.8
5.5
3.4
4.7
3.5
+0.1^
0.4
1.3
0.9
1.4
3.3
Feb.
(percent
7.5
7.9
9.6
6.7
7.2
10.6
2.3
2.0
3.1
2.6
3.0
6. -5
May
net weight
2.7
2.7
3.8
1.8
3.0
5.1
0.02
•K).5i/
0.8
0.3
0.7
3.8
July '76
loss)
15.3
17.9
16.3
14.3
16.1
17.5
9.3
11.6
11.3
11.4
12.6
13.8
July '77
29.7
25.2
-I/
22.7
22.9
—
16.02/
23.0
—
18.9
22. Oy
—
i/Weight gain noticed
I/Estimated from A or B horizon samples
VSamples lost from B horizons for last sampling date.
109
-------
30-
S O N D J
1975
F M A M J J A
1976
J J A
1977
Figure 21. Changes in net weight of wood blocks on top
of the litter over time by sludge treatments.
110
-------
exposure, wood blocks in the 3QO plot gained Q.1% i;n weight, while 300W lost
0.9% in weight. During the winter from October to February, decomposition
continued in both the control and 100 plots (2.9% and 3.3%) and was initiated
in the 300 and 300W plots (2.4% and 1.7%).
Decomposition was evidently arrested between February and May as all
plots showed an increase in net dry weight of exposed wood blocks. The
consistency of this phenomena suggests rapid growth of fungal hyphae with
translocation of metabolic products into the wood blocks. Large net weight
losses between May and July indicate accelerated rates of decomposition. Net
weight loss was 12.6%, 12.5%, 9.3% and 11.1% for L layer blocks, in the con-
trol, 100, 300 and 300W plots, respectively.
Decomposition on the control plot was significantly greater (14.4%) the
following year than in sludge treated plots (TOO plots, 8.4%; 300, 6.7%; and
300W, 7.5%).
Decomposition in A Horizons
Patterns of decomposition from September 1975 through July 1976 in A
horizons were very similar for the control and 100 sludge plots (17.9 and
16.1%). Both had more rapid decomposition than the 300 and 300W plots (11.6
and 12.6.%). From September through May, heavy sludge applications (300 and
300W plots) impeded decomposition in soil A horizons, while the trend of
initial accelerated decomposition (Sept. through Feb.) was again reversed in
the February through May period with a weight gain (+0.5%) on the 300 plot.
All plots showed significant decomposition between May and July; control
plot, 15.2%; 100, 13.1%; 300, 12.1%; 300W, 11.9%.
Decomposition continued at a reduced rate for the next year in control
and 100 plots (control, 7.3; 100, 6.8%). Accelerated decomposition occurred
on the 300 series plots with a weight loss of 11.4% in the A horizon of the
300 plot and estimated at 9 .4% for the 300W plot.
Decomposition in B Horizons
Again, samples were lost for the final sampling period of the soil B
horizons; however, trends in the data suggest the results should be very
similar to decomposition in soil A horizons. Decomposition trends of control
and 100 plots are very similar, as are plots 300 and. 300W, and significantly
different from A horizons.
Ill
-------
Section 26
EVERETT SOILS, VIRUS AND BACTERIA
Sampling either the soil or soil solutions for virus and bacteria is
complexed by the interaction of these organisms with the soil or soil solu-
tion sampling system. Swartz1, in a study of retention of coliform, strain,
E.coli by lysimeter plates concluded that bacteriological data derived from
sampling soil solutions with lysimeter plates is of questionable value. He
identified very marked retention of bacteria in the plates. For example, a
control solution containing 1.2 x 106 organisms were passed through 6 differ-
ent lysimeter plates. Colonies in the extracted solution varied from 0 to
1.2 x 103, a reduction of 1000-fold greater in the numbers of colonies.
With these limitations in mind, the following information was developed
in this study. Soil samples in the upper 5 cm from control plots developed
430 colonies of total coliform per gram of wet weight. Composite soil solu-
tions typically average less than 20 organisms of total or fecal coliform
per 100 mis. No significant differences were found between control and sludge
piots.
Litter surfaces have 4.3 x 10^ colonies per gram of wet weight immedi-
ately after spray irrigation. Coliform are evidently endemic as resampling
of early sludge application on plots which studied methods of sludge applica-
tion retained 3.9 x 104 colonies per gram of wet weight.
Soils and soil solutions analyzed for other bacteria and virus by the
Virology Lab of Children's Orthopedic Hospital have not identified virus in
any samples. Unidentified bacteria have been found throughout the soil
profile. Results to date suggest that experimental designs which utilize
aluminum oxide lysimeters may produce questionable results for study of
bacteria and virus in forest soils.
1R. Swartz, Bacteriological Evaluation of Lysimeter Plates, Metro memo
(April 18, 1975) to G. Farris and R. Domenowske.
112
-------
Section 27
EVERETT SOILS, HEAVY METALS
The fate of heavy metals in the Everett soils is somewhat complex. It
may be assumed that acid Northwest forest soils have a very strong affinity
for heavy metals and provide excellent renovation. This conclusion is sup-
ported by certain analytical data; however, the exact value of these field
data is unknown.
Earlier laboratory experiments with tension lysimeter plates indicate
aluminum oxide, like soil, has an affinity for many heavy metals and will
remove certain heavy metals from the soil solution as it passes the plate
In the laboratory, known concentrations of heavy metals were passed through
lysimeter plates, and the recovery in the extracted solution determined The
following briefly summarizes the results (all values in mg/1).
Original Solution
Cu
0.18
Cr
0.18
Cd
0.036
Pb
0.19
Ni
0.20
Zn
0.048
Extracted Solution <0-01 <0'01 <0-004 °-06 <0-°2 0.039
There was variation in retention by individual plates, suggested to be a
function of the aluminum oxide matrix making up the plate. The strong inter-
action of solution concentration and affinity of heavy metals for aluminum
oxide would make interpretation of field soil solution data for heavy metals
impossible. Trace concentrations of the above heavy metals were found in
soil solutions extracted in the field. Interpretation of these data is
impossible at this time.
113
-------
Section 28
SLUDGE APPLICATIONS AND FOREST GROWTH
Even the relatively uniform second growth Douglas-fir stand selected for
sludge application treatments had high variability between average diameter,
numbers of trees per plot, and average growth rates by plots (Table 28).
Applications of sludge did not significantly alter tree growth as
studied by growth on a plot basis. Analysis of variance showed no treatment
effects when tested as a difference between treatment means. The analysis
of variance tested plot means for effects of sludge treatments with two
replications using DBH or periodic annual increment (pai) after irrigation
minus DBH or pai before irrigation as the test parameter.
df
SS
MS
Between treatments
Error (within treatments
TOTAL
3
4
7
0.48375
1.91500
2.39875
0.16125 0.3368
0.47875
NS
(a=0.10)
where
standard error of difference = 0.49 mm
coefficient of variation = 73.8%
The large error (within treatment) indicates the variability within
treatments is greater than the variability between treatments (Table 28).
Numbers of trees per hectare varied from 963 (390/ac) on the control plot to
over 2000 (810/ac) on a 200 series sludge plot. The usual inverse relation-
ship between numbers of trees and DBH is apparent. The control plot averaged
21.5 cm (8.5 in.) in diameter while the 200 series sludge plot averaged 14 cm
(5.5 in.). Basal area and volume are frequently less variable than the
numbers of trees or their average diameters. Basal areas ranged from 35.0 to
43.8 mz/ha (151 to 191 ft2/ac.). Volumes ranged from 305.3 to 455.9 mVha
(4363 to 6515 ft3/ac.).
The post treatment results (Table 28) exhibit similar patterns of large
variation between plo'ts; however* mortality on plots with numerous trees (200
plot) reduced the ratio considerably.
Gross pai also varied considerably for all plots before and after treat-
ments (Table 29). Average annual increments for all treatments generally
114
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increased between 1975 and 1977 as compared to the pretreatment period, 1970
to 1975, the control plot. Increased growth rates are probably due to the
aerial fertilizer application in March 1974 and/or summer rainfall in 1975.
SLUDGE APPLICATION AND FOREST GROWTH, PAIRED TREES
I.
The average pai for all plots is summarized in Table 30. Analysis of
variance showed significant difference in growth rates when tested using
paired trees. For most parameters tested, growth rates nearly doublediwhen
comparing 1970-75 rates with 1975-77 rates.
!
Table 31 uses regression analyses to compare paired tree growth for
sludge treated, water only, and control plots for diameter, basal area! and
volume growth. The 200W treatment significantly increased diameter, basal
area, and volume growth for both the 2 and 3-yr. growing periods.
The 300W treatment increased diameter growth in the 1975-76 year and
increased basal area and volume growth for all years. Volume growth for all
analyses was significantly increased for all sludge treatments except the
300 for 1975-77. :,
Irrigation with water only did not increase growth over the control
(Table 31). I
DIAMETER GROWTH RATE, PAIRED TREES
An analysis of variance for paired trees within treated plots and the
control used DBH pai after treatment minus DBH pai before treatment as a test
of change in growth rate. Sludge applications significantly increased
diameter growth rate at the 95% confidence level-(Table 30).
Source of Variation df SS MS
Between treatments
Error (within treatment)
TOTAL
4
168
172
33.359
534.948
568.307
8.3398 2.62*(a = 0.
3.1842
05)
Simple linear regression equations were developed from these paired
individual trees (Table 2, Appendix C). Equations for pretreatment growth
over initial size were compared with the control and were found to be hbmoge-
nous. Therefore, the use of pretreatment pai as an independent variable in
the other equations tested is not confounded by pretreatment growth differ-
ences, and treatment effects can be assessed (Table 31)." I
Comparisons of diameter growth showed 2 years of sludge applications
(200W and 300W) significantly increased diameter growth rates over control
After 3 years of irrigation only, the 200W treatment had significantly greater
diameter growth rates. Growth rates after 3 years of irrigation as a function
of before irrigation growth are shown in Figure 22 for 200 W and control
117
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trees. Slopes show a significant treatment effect for only the 200W sludae
treatment.
BASAL AREA GROWTH RATE, PAIRED TREES
Basal area growth for individual paired trees showed trends similar to
DBH growth. All sludge plus water treatments (100W, 200W and 300W) had sig-
nificantly greater basal area growth rates than control trees after 2 years
After 3 years, only the 200W and 300W treatments maintained significantly
greater growth rates. Growth during the 3 years of treatment, as a function
of pretreatment basal area pal, is shown in Figure 23. Slopes of basal area
growth rate were significantly different with the 200W, 300W treatments
having the greatest growth rates. Again, the sludge plus water treatments
all had increased growth rates over sludge only treatments (Table 31).
VOLUME ANALYSIS
Volume growth of all sludge treated trees was significantly greater than
the control trees after 2 years. However, the 300 treated trees did not con-
tinue to show greater growth rates at the end of the third year.(Table 31).
WATER ONLY IRRIGATION, GROWTH, PAIRED TREES
Water only irrigation did not significantly alter growth rates, whereas
water plus sludge did (Table 31). Actual growth in DBH, basal area, and
volume are almost identical for the paired tree analyses.
SLUDGE VS. SLUDGE PLUS WATER, GROWTH, PAIRED TREES
Growth comparisons of sludge treated trees versus sludge plus water
treated trees (Table 32) indicate sludge treatments followed by water signi-
ficantly increased tree growth rates. Growth rates of trees receiving water
plus sludge treatments seem to increase with increased sludge applications.
Adjusted diameter pai (mm per year) as a function of weekly irrigation
rates (cm) over 3 years (Figure 24) shows sludge increased diameter growth.
When sludge is followed by water, diameter pai growth increased up to 25%
over control diameter pai at a weekly irrigation level of 0.5cm (0.2 in.) and
then growth decreased slightly with increased irrigation.
Results from this limited study indicate that irrigation with stabilized
municipal-industrial sewage sludge has increased the growth rate of indi-
vidual paired trees. The 200W had the greatest'.effect on growth. Generally
the addition of water applied after sludge irrigation significantly increased
growth over sludge-only irrigation. Therefore, to obtain the maximum growth
effect of sludge application, a water irrigation treatment would be recommend-
ed to wash the sludge into the rooting zone.
Disposal of sewage sludge on this forested site has apparently had a
positive effect on increasing tree growth. However, longer term studies are
needed to assess impacts on soils, chemical breakdown of grease and hair
121
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124
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applied, and impacts on microbial populations, before this technology becomes
a standard siIvicultural tool for intensive forest management.
125
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Sectton 29
DISCUSSION OF SLUDGE APPLICATIONS TO FOREST SOILS
A discussion evaluating the results of three years of testing of sludge
applications in the forest must be concerned with: First, is it economically
feasible as a potentially useful method; and second, what are the environ-
mental consequences, particularly potential eutrophication of ground water?
The following sections contain both a discussion and conclusions relative to
the impacts of sludge applications. Few equivalent studies are available for
comparison with these results.
SLUDGE APPLICATION METHODS
Disposal of sludge in Pacific Northwest forests could have either of two
major objectives. A community or outlying urban area might have an objective
of the disposal of maximum amounts of sludge on a minimum forest area.
Investments in forest land and irrigation system would be minimum. 'In this
case, the community would like to apply the maximum quantity of sludge per
acre per year without degradation of environmental quality or eutrophication
of ground water.
On the other hand, the forest industries might be interested in inten-
sive management of a substantial forest acreage with the prime objective of
accelerated forest growth. In this case, the enhancement of growth from both
applied water and sludge would be spread over a many-fold greater area and
use a greatly diluted sludge and a substantial quantity of effluent treatment
water.
In either case, an effort would be made to keep capital investments to a
minimum in the sludge application systems. This research concludes that
spray irrigation is one of the most effective and possibly efficient means of
distribution of sludge in the forest environment. Spray irrigation of sludge
may be achieved from mobile tankers, such as truck-mounted units, under-the-
canopy spray irrigation as used in this study, or over-the-cariopy with the
large high-powered water canons.
Costs of development of irrigation systems for sludge application to
forests may be estimated to a degree by the costs of similar developments for
agricultural land. Troemper (1974) developed a spray irrigation system for
application of 12.1 cm (4-75 in.) of anaerobically digested sludge at a cost
of $17,900/ha($7245/ac.). The system installed included pipe, sprinkler, a
pumping system, a drain system to intercept soil solution percolate for
126
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recycling. Average costs for sludge disposal by the system were $56.02 per
thousand gallons of sludge (about $260/dry ton at 5% solids in sludge).
Costs of installing a forest irrigation system would vary depending on
soil types, slopes and the forest stand. Estimated costs for a system as
used at Pack Forest, including pipe, sprinklers, drain valves and certain
soil water monitoring equipment, are $5000/ha ($2000/ac.) for application of
13.3 cm (5.25 in.) of 3% solids sludge or an average cost of $14 per thousand
gallons. These costs do not include the pumping system or delivery of sludge
to the disposal site. Obviously, the costs of pumps and/or transportation
of sludge to the disposal site could be highly variable but probably could be
capitalized over a long-term application. A minimum cost of $110/dry ton is
projected based on above cost estimates, not including a pump or hauling.
Installation of a sludge application system before establishment of the
young forest would probably be the most economical. Heavy equipment could be
used for burying the pipe without damage to the forest stand. As the young
forest grows, a supply of water may be necessary to wash sludge from the
foliage after each sludge application.
Piping at Pack Forest rested on the soil surface. Burying would be an
improved alternative for a permanent system but would also add to the cost.
It would have the advantages, however, in preventing freezing as well as
gradual deterioration of the surface pipe and restrictions imposed on moving
equipment through the forest because the pipe is on the soil surface.
In a system where uniform application of sludge is not necessary, more
efficient distribution could be achieved with the use of large water canons.
Sludge would be applied followed by water to wash sludge from tree crowns.
RATES OF SLUDGE APPLICATION
First year sludge applications in this study were obviously too large.
Impeded infiltration occurred after sludge applications exceeded 25 cm (10
in.). Excessive amounts of nitrogen applied resulted in a very large total
loading with rapid conversion to nitrate forms and leaching in the soil solu-
tion. The reduced rates which applied from 10 to 40 mt/ha (4.5 to 18 t/ac.)
appear to be a reasonable range of sludge loadings. For the three soils,
Everett, Mashel and Wilkeson, loadings varied from 4.8 to 29.8 mt/ha/yr
(2.1 to 13.3 t/ac/yr). Physical renovation by each soil for the loadings
through the given range was excellent. The total organic carbon analyses
indicated no contamination within the soil profile of materials in sludge.
The original Everett soils plots had sludge applications ranging from
45 to 108 mt/ha (20 to 48 t/ac) during the study. The physical renovation
capacity for selectively filtering solids was still excellent on completion
of the study. Careful analyses of sludge composition are required to estab-
lish average solid content of sludge in designing a system and rates of
application. This study anticipated and designed for an average solids con-
tent of 2.1%, assuming random variation during the life of the study. Solids
actually averaged 3.2% over the life of the study; thus, design applications
for a depth of sludge had significantly'greater loadings of solids than
127
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anticipated. In most cases, rates of sludge application to a given area will
not be limited by quantities of solids but rather by the chemical constitu-
ents.
RENOVATION OF NUTRIENTS
Intensive management of second growth forest stands often requires
application of numerous chemicals for control of insects, competing brush
species, and in recent years, fertilizers to accelerate forest growth.
Foresters are concerned with the fate of applied chemicals and potential
environmental impacts, particularly in the hydrologic system from the soil
solution to ground water or streamflow. Detailed forest ecosystem studies
have identified nutrient leaching (Cole, et al. 1976) and impacts of forest
fertilization (Gessel and Cole, 1965).
Sludge applications of this study provided nutrients in quantities
greatly in excess of most other cycling studies of either fertilization or
waste water management.
RENOVATION OF BASE NUTRIENTS
The renovation capacity of the three soils studied has been expressed as
the percentage of retention of the total applied nutrients. In general, the
percent renovation capacity for base nutrients is excellent, expressed as a
percentage. Renovation by the soil retains large quantities of nutrients in
the soil profile, but when very large quantities are applied, the flux or
loss from the soil profile could still be significant. For example, the
original 200 series plots on the Everett soil received 80.7 mt/ha (36 t/ac)
of base nutrients. Renovation was 96% of that applied; however, 3.2 mt/ha
(1.4 t/ac) did leach below the 2 mm (7 ft.) depth in the soil profile.
Analyses of the dissolved chemicals in ground water in wells adjacent
to the plots did not reveal a trend of increasing dissolved calcium or other
base nutrients in ground water. Maximum concentrations of calcium found in
the soil solution of sludge treated plots ranged to 14 times that of the soil
solution of control plots.
Maximum base nutrient concentrations in the soil solution were observed
during driest portions of the summer. Fall rains increased the supply of
soil water, thus, diluting the nutrient concentrations. It is expected that
flux of the soil solution to ground water transporting the dissolved nutri-
ents would then be greatly diluted, thus, resulting in insignificant changes
in the composition of dissolved ions in the ground water. Calcium was
applied in largest quantities and had the largest flux through the soil pro-
file of any of the base nutrients. Concentrations of magnesium, potassium
and sodium were greatly reduced in the ground water, and frequently were only
a few-fold greater than concentrations in the soil solution of any control or
water plots. In fact, the highest concentration of potassium found in any
plot was in the soil solution of the control plot.
128
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RENOVATION OF PHOSPHORUS
Renovation on all soils and plots of total P and P04-P was consistently
excellent. The maximum loss was on the Mashel soil (30 series application)
where a flux of 5 kg/ha/yr (4.5 Ibs./ac./yr.)- was identified when 432 kg/ha
(385 Ibs./ac.) of total P had been applied. On the Everett series, after
three years of sludge application with quantities of total P applied in
excess of 2 mt/ha (1 t/ac.), losses were a maximum of 2.0 kg/ha (1.8 Ibs./
ac.).
Large quantities of total "P and PO^-P can be applied to forest soils
without impacts on ground water or the soil solution.
RENOVATION OF NITROGEN
Nitrogen may well be the most critical element in land disposal of
sludge, either forests or agricultural. Concentrations of nitrogen are
frequently high in sludge, ranging from 0.9 to 1.8% in this study. The soil
solution and organisms in the forest soils provide environmental conditions
for a very rapid conversion of total N or NH4-N forms to N03~N. Frequently,
the renovation of Nfy-N appears excellent (ranging from 80 to 99+%). However,
soil chemical reactions convert NH/pN to N03-N with subsequent leaching,in
the soil solution, making contributions of N03 to ground water one of the
most important implications in land disposal of sludge.
The underestimation of the average total N composition of Metro sludge
resulted in large total nitrogen applications. The original Everett plots
received 5.3 mt/ha (2.4 t/ac.) of total N in the 300 series with renovation
of 70% (1.6 mt/ha; 0.7 t/ac. lost). Renovation by other plots was consider-
ably less. The 200 series plots received 4.9 mt/ha (2.2 t/ac.) over the
three years and had a flux of 4.7 mt/ha (2.6 t/ac.), achieving 3% renovation
(Table 6).
The flux of nitrogen from the soil profile is dominated by water soluble
N03-N. In the previous two examples, the total N flux of 1.6 mt/ha (0.7
t/ac.) on the 300 series plots was accounted for by 1.4 mt/ha (0.6 t/ac.) of
N03-N. The 200 series plots had a very similar percentage N03-N flux. Of
the 4.7 mt/ha (2.1 t/ac.) flux, loss of 4.0 mt/ha (1.8 t/ac.) -was NOo-N
(Table 6).
Renovation of NH4-N is excellent in these forest soils. A maximum loss
of 290 kg/ha (259 Ibs./ac.) was measured on the 100 series Everett plots
which had received 1.4 mt/ha (0.6 t/ac.) of NH*-N. The range for the rest
of the original plots was from 1 to 31 kg/ha (0.9 to 28 Ibs./ac.) over the
three years of study of the original series of plots. The new series of
plots established on the Everett, Mashel and Wilkeson soils had maximum NH^-N
flux of 59 kg/ha (53 Ibs./ac.) on the 30 series plots on the Mashel soils
(Table 19). A range of near zero to 43 kg/ha (38 Ibs./ac.) occurred witn the
other soils and plots. The Everett soils had the best overall renovation with
6 kg/ha (5 Ibs./ac.) occurring on the 40 series plots where the applied
quantity was 828 kg/ha (739 Ibs./ac.)(Table 12).
129
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A volatilization loss of NH4-N, identified by odor, was often noticed
as spray irrigation of sludge commenced. Forms other than NH4-N and N03-N of
nitrogen in sludge were not identified. Nitrification processes with expo-
sure of the anaerobically digested sludge to oxygen suggest a dynamic
mechanism of conversion in form. Alexander (1965) studied nitrification
reactions identifying exothermic and chemoautotrophic along with the groups
of micro-organisms involved in biosynthetic reactions. The oxidation of
NH4-N is:
then
2NH4 + 302 = 2N02" + 4H
2N0
= 2N0
Micro-organisms required for the above process are Nitrosomnoas and
Nitrobacter. Processes of oxidation of NH4-N are very rapid as conversion of
total N and NH4-N proceeded rapidly enough that significant increases in
nitrogen could not be identified in the soil profile in the second year
(Table 8). Third year analyses of Everett soils, however, did indicate
increased concentrations of total nitrogen in the forest litter layer and the
soil A horizon (Table 10). All sludge treated plots were averaged and tested
against the pretreatment analyses to identify this significant increase in
total N.
Reduced rates of sludge application (10-40 plot series) had best total
nitrogen retention on the Wilkeson soils (average 79%) with the Mashel and
Everett averaging 69 and 55%, respectively. Trends to increasing quantities
of soil nitrogen are indicated in all three soils; however, differences are
not quite statistically significant (Tables 13, 20 and 23). Retention of
nitrogen applied to the soil ranged from 111 kg/ha (99 Ibs/ac) on the Mashel
soil (10 series plots) to 1026 kg/ha (914 Ibs/ac) on Everett soils (40 series
plots). In the forest ecosystem, conservation of nitrogen is related to
accumulation of carbon. Micro-organisms decomposing the carbon supply require
nitrogen for vital life processes. A large supply of available soil carbon
frequently indicates a'limited supply of available nitrogen to micro-organisms.
Applications of sludge provide a readily available source of nitrogen
accelerating plant growth. As additional amounts of organic debris become
available for decomposition from stimulated growth, the soil nitrogen will
accumulate increasing amounts of total N.
The carbon-nitrogen ratio is an interaction of both the quantity of
organic carbon, and the amount of total nitrogen shows wide variation on
sludge plots at this time. The fine textured Mashel and Wilkeson soils had
marked increases in the carbon-nitrogen ratio of the forest litter layer
(from 31:1 to 70:1 for the Mashel and 38:1 to 68:1 for the Wilkeson).
Increased organic matter occurred in L layers on these two soils without sig-
nificant change in total N percentage. These data suggest that both soils
will accumulate nitrogen until the carbon-nitrogen ratio is reduced.
The very coarse textured Everett soil had slight reductions in the
organic matter content of the forest'litter layer and A horizon. Nitrogen
130
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contents did not change significantly, thus, a slight reduction in the carbon-
nitrogen ratios following sludge applications. Applied sludge and water
should accelerate forest .ecosystem productivity, thus, increasing the supply
of carbon. With time, increased growth will increase carbon supplies and
provide the mechanism for increasing the quantities of nitrogen stored in the
forest floor and soil.
Quantities of NOs-N have increased significantly in the soil solution as
compared with the control and water plots. As with base nutrients, maximum
concentrations occur during times of minimum soil water, thus, greatly concen-
trating both N03-N and total N concentrations. Rainfall or irrigation
increases the supply of soil water, diluting the concentration of dissolved
materials. The dissolved chemistry of ground water (well water) does not
reveal any significant trends or a departure from normal concentration over
time.
EVALUATION OF TOTAL ORGANIC CARBON
The trend to increasing quantities of the soil organic matter is verified
by the analyses of total organic carbon (TOC). Increases in TOC in the C
horizon with sludge applications were identified; however, analyses detected
only natural decomposition organic compounds. These compounds were also
identified in the ground water well samples. Large applications of sTudge
(45 to 108 mt/ha; 20 to 48 t/ac.) have not increased organic matter contents-
of the forest litter layers (Table 10). This suggests a marked increase in
biological decomposition of fine or colloidal organic materials. TOC analyses
also identify increased metabolism when sludge is applied. Marked increases
in amounts of aliphatic fatty acids found in the soils are related to acids
of normal metabolic products of micro-organisms. Increases in TOC appear to
be the result of increased metabolic activities and do not represent, for an
example, the appearance of refractory compounds in the ground water resulting
from sludge applications.
EVALUATION OF BIOLOGICAL DECOMPOSITION
Rates of biological decomposition depend on inherent organic matter
structure and chemical composition, decay organisms, and environmental condi-
tions, interacting with action of extra cellular enzymes and physical
weathering. Processes which degrade wood include immobilization, incorpora-
tion, leaching, physical damage and enzymatic dissolving. Tests used in this
study include relative weight changes and the solubility of woody material in
V/o NaOH. Relative changes in weight loss do not accurately measure the
decomposition process, as identified in this study. Frequently, there is a
slight gain in block weight attributed to micro-organisms invading the wood
sample. This occurred on the 300 series plots (Table 27) and is suggested by
the decrease in solubility of. .the wood blocks over time when extracted with 1%
NaOH. With initiation of the growing season in May 1976, 'rates of decomposi-
tion as measured by both weight loss and soda solubility increased rapidly.
There are apparently no significant differences between treatments for the
duration of the study (July 1977). However, some differences in- response by
horizons were noted.
131
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SLUDGE APPLICATIONS AND FOREST GROWTH
The study of forest growth by plots and treatments yielded negative
responses to sludge applications. Statistically significant increases in
growth could not be identified because of the very high variability in num-
bers of trees, sizes and basal area from plot to plot.
Re-analysis of the data on a paired tree basis using trees of-approxi-
mately equal growth rate and initial diameter developed significant growth
responses from sludge applications. The addition of water after sludge irri-
gation provided the most significant growth increases. The applications of
sludge alone significantly increased growth over the control or water
irrigated treatments.
Though the short-term results of sludge treatments to forest trees show
promising growth acceleration, several important questions remain to be
answered. Chemical breakdown of suspended materials in sludge should occur
in a short time. If greases, hair, etc. are not attacked by microbial popu-
lations, then accumulations could be detrimental. To date, heavy metals seem
to be no problem. In a highly organic system, they should be effectively
chelated or fixed in the soil. Applied water and nutrients should stimulate
biomass productivity, increasing the production of carbon which would allow
greater retention of nitrogen. Increased quantities of nitrogen would con-
tinue to provide accelerated growth, thus, increasing ecosystem productivity
over the long term.
132
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Section 30
SUMMARY OF RESULTS OF SLUDGE APPLICATIONS
The initial very large amounts of sludge application to the 200 and 300
series Everett soils resulted in ponding of sludge on 5 to 25% of the surface
area of certain plots. Even these very large applications did not result in
noxious odors nor a generally unsightly condition in the forest. Reduced
rates of sludge application (10 to 40 mt/ha/yr or 4.5 to 18 t/ac.) are almost
unobservable. Excellent renovation of suspended and dissolved materials in
sludge has been achieved with the exception of nitrate nitrogen. All rates
of sludge application have resulted in significant nitrification and leaching
of NOs-N in the soil solution. Ground water samples taken from wells at over
,10 m (30 ft.) deep show no enrichment in dissolved ions from sludge applica-
tions. Significant renovation takes place in the surface 2 m \1 ft.) of
the forest soil. It is quite possible that the additional 8 m (26 ft.)
between the deepest sampling and the ground water table continue to renovate
the soil solution.
X
Impacts of nutrient flux through the soil profile to ground water and/or
the stream will require studies on a watershed basis.
A few significant changes in soil chemical properties were identified.
While statistically significant, the ecological significance is as yet
unknown. Cation exchange capacity was frequently the most significantly
influenced soil property. Sludge applications generally increase cation
exchange capacity of the forest litter layer and the A horizon. A general
trend to increasing soil organic matter, decreasing pH, and increasing total
cation exchange capacity has been identified. Large applications of calcium
have generally resulted in increases in exchangeable calcium in litter and A
horizons. Other changes in exchangeable cations are sporadic—statistically
significant, but again ecologically inconsequential.
Modified rates of sludge application in the range of 10 to 30 mt/ha/yr
(4.5 to 13 t/ac./yr.) could be received by many forest soils. Additional
quantities of waste water applied following sludge applications would be
beneficial. Further research should isolate impacts on a watershed basis to
evaluate leaching to ground water and potential eutrophication of streams.
This short-term study did not identify significant increases in forest
growth on a plot basis. Natural variability in stand densities and growth
rates obscured short-term growth responses. A more sensitive analysis of
paired trees of equal size resulted in significant growth increases of the
oaired tree receiving sludge applications. Sludge applications followed by
133
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water seemed to be the most beneficial with the 200W treatments probably
enhancing forest growth to the greatest extent. Longer term studies are
necessary to adequately answer questions relative to long-term impacts of
sludge application in the forest environment. These studies, if conducted
on a watershed basis, would have the opportunity for a greatly expanded plot
network for sludge versus no sludge treatments.
This short-term study of sludge applications in the forest, provides
encouraging results for the ability of forest soils to renovate constituents
in sludge, along with initial indications of enhanced forest growth based on
paired tree comparisons. It is also encouraging that human pathogens of the
bacteria and virus natures were not isolated, and heavy metals were either
absorbed in the aluminum oxide lysimeter plates or tied up in the soil
profile.
134
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LITERATURE CITED
Aldrich Chemical Company. 1969. Diazomethane. Aldrich Chemical Co.,
Milwaukee, Wis. 4 pp.
Alexander, M. 1965. Nitrification in Soil Nitrogen, ed, W. V.
Bartholomew and F. E. Clark. Amer. Society of Agronomy. Madison,
Wis. 615pp.
American Standard for Testing Materials (ASTM DI758-60T). 1961. Evalu-
ating wood preservatives by field tests with stakes. Amer. Society
for Testing and Materials. Philadelphia, Pa. ppl003-1012.
Braids, 0. and R. Miller. 1975. Fats, waxes and resins. IN; Soil.
pp343-368 IN: Soil Components, Vol. 1, J. Gieseking (ed). Springer-
Verlag, New York, N. Y. 526pp.
Bremner, J. M. 1965. Total nitrogen. IN: Methods of Soil Analysis,
Part 2. Chemical and biological properties. Am. Soc. Agronomy,
Madison, Wis. ppl149-1!60.
Cole, D., S. Gessel, L. Fritschen, B. Hrutfiord and P. Schiess. 1976.
A study of the interaction of wastewater with terrestrial ecosystems.
U.S. Army Corps of Engineers, Wash., D. C. 170pp.
Cowling, E. B. 1962. Comparative biochemistry of the decay of sweetgum
sapwood by white rot and brown rot fungi. USDA technical bulletin
No. 1258. ppl-79.
Dice, S. F. ,1970. The biomass and nutrient flux in a second growth
Douglas-fir ecosystem; a study in quantitative ecology. Ph.D. thesis.
Univ. of Wash., Seattle. 165pp.
Forest Soils Committee of the Douglas-Fir Region. 1953. Sampling procedures
and methods of analysis for forest soils. Univ. of Wash., Seattle. 38pp.
135
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Gessel, S. P. and D. W. Cole. 1965. Influence of removal of forest cover
on movement of water and associated elements through soil. Journ. of
Amer. Water Works Assoc., 57:1301-1310.
Gieseking, J. (ed) 1975. Soil Components, Vol. 1, Springer-Verlag, New
York, N. Y. 526pp.
Goring, C. and J. Hamaker. 1972. Organic chemicals in the soil environ-
ment. Marcel Dekker, New York, N. Y. 968pp.
Jackson, M. L. 1958. Soil chemical analysis. Prentice-Hall, Inc.
Englewood Cliffs, N. J. 498pp.
Lenette, E. H. and N. J. Schmidt. 1969. Diagnostic procedures for viral
and rickettsial infection. Amer. Pub!. Health Assoc., 946pp.
Minyard, P. and C. Driver. 1975. Methods of analyses for biological
decomposition of wood. Unpublished. Univ. of Wash., Seattle.
Pacific Northwest River Basin Commission. 1970. Water Resources -
Appendix V - Columbia-North Pacific Region Comprehensive Framework
Study. Pacific Northwest River Basins Commission.
Schlichte, A. K. 1968. Mineralogy of the Everett Soil. M. S. Thesis.
Univ. of Wash., Seattle. 59pp.
Schnitzer, M. and S. Kahn. 1972. Humic substances in the environment.
Marcel Dekker, Inc., New York, N. Y. 327pp.
Soil Conservation Service. 1973. A soil survey of King Co. Washington.
Washington Agricultural Experiment Station. 100pp.
Standard Methods. 1971. J. Taras, A. E. Greenberg, R. D. Hoak, and
M. C. Rand (eds.), Amer. Pub. Health Assoc., Wash., D. C. 874pp.
TAPPI Standard (T4m-59). 1961. One percent caustic soda solubility of
wood. Technical Assoc. of the Pulp and Paper Industry. New York,
N. Y.
TAPPI Standard (Tllm-59}. 1961. Sampling and preparing wood for analysis.
Technical Assoc. of the Pulp and Paper Industry, New York, N. Y,
136
-------
Troemper, A. P. 1974. The economics of sludge irrigation. IN: Municipal
Sludge Mgmt., Proc. Nat. Conference. Sponsored by Office of Research
and Dev., U. S. Env. Prot. Agency, Env. Quality Systems, Inc. and
Information Transfer, Inc. 257pp.
Walkley, A. and C. A. Black. 1934. An examination of the Degtjareff
method for determining soil organic matter, and a proposed modifi-
cation of the chromic acid titration method. Soil Sci. 37:29-38.
137
-------
APPENDIX A
Computer printout of all soil solution analyses by treatments, sample
date, cm of sludge, water and precipitation for sample period, sample pH,
total nitrogen, ammonium nitrogen, nitrate nitrogen, total phosphorus, ortho-
phosphate phosphorus, sodium, potassium, calcium and magnesium as mg/1,.
Wonly = water
Contl = control !
= 40 on Everett
S25
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S75
S75W5
P21
P22
P23
P24
P31
P32
P33
P34
P41
P42
P43
P44
= 100
= 100W
= 200
= 200W
= 300
= 300W
= 40 i
= 30
= 20
= 10
= 40 i
= 30
= 20
= 10
= 40
= 30
= 20
= 10
= 40 on Wilkeson
138
-------
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APPENDIX B
A computer program was written to automatically plot conductivity,
temperature, dissolved oxygen and pH for data recorded on mag tape from the
Metro-data units. Several scans were run during initial stages of the
project. Large short-term variations in monitored parameters were found,
particularly in the forest litter and soil A horizons. For the scans used
as an example in Figures B-l to B-4, 0 hours were mid-day on a warm day in
mid-June. An irrigation with sludge and water took place at about 18 hours.
Temperature was depressed, conductivity increased, dissolved oxygen increased
and pH was significantly depressed in the litter layers.
FIELD RECORDING OF SOIL SOLUTION PARAMETERS
Soil solution extracts from the lysimeter plates at various depths were
passed through sensing cells where temperature, dissolved oxygen, specific
conductivity and pH were recorded at 10-minute intervals. Data were recorded
on Metro-data magnetic tapes which were programmed for display of average
hourly values through computer printout. A complex scaling format provided
for scaling each variable between its maximum and minimum range for the dura-
tion of a scan. Computer output for simultaneous runs of the litter, A, B
and C horizons is shown in figures in Appendix B. Figure B-l (forest litter)
shows diurnal variation in soil solution temperature (T), scaled from 6.38°
to 14.76° C. The line D shows parts per million of DO cencentration varying
from minimum values of 6.23 to 9.36 mg/1. The C line is micromhos of
specific conductivity with variation from 76.3 to 125.9. Soil solution pH
(P) is scaled from 6.38 to 8.72. The inverse relationship between DO and
temperature shows daily periods of maximum temperature, show minimum DO
levels, and inversely hours of coldest temperature show maximum DO. pH and
conductivity generally show similar trends, though different magnitudes of
change, suggesting that bicarbonate is probably influential in pH measurement
with increasing quantities of free ions releasing additional cations to
solution.
The four figures show declining variability in each parameter with
increasing depth, as upper soil horizons and litter layers are the most
dynamic. At lower depths, there is less variation in temperature, DO and
conductivity.
151
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154
-------
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• 3
155
-------
APPENDIX C
*i*
Pretreatment diameter equations based on increment cores. •
Initial diameter measurements of the Pack Forest Sludge Project began
after the 1974 growing season. At that time, increment cores were taken; from
ten trees per plot. The sample of ten was to be representative of the plot:
four site trees, two trees of'intermediate diameter, and four trees represent-
ing the lower diameter classes. , :.
X-ray photos were taken of each increment core and measurements were
obtained from these photos. The measurements, to the nearest 0.02 in.,, '
represented the last 2, 5, and 10 years of growth for each tree.
Marshall Murray's Inside and Outside Bark DBH Equations for Plantation
Douglas-fir (shown below) were used to transform the increment core measure-
ments to DBH outside bark (o.b.).
DBH (o.b.) * .920 = DBH inside bark (i.b.)
DBH (i.b.) * 1.088 = DBH outside bark (o.b.)
Shown below are the steps taken to calculate DBH (o.b.) for the years
1964, 1969 and 1972. These steps were repeated for each individual tree-.
Step 1. 1974 DBH (o.b.) * .920 = 1974 DBH (i.b.)
2. 1974 DBH (i.b.) - (2-yr. increment * 2) = 1972 DBH (i.b.)
3. 1972 DBH (i.b.) * 1.088 = 1972 DBH (o.b.)
4. 1974 DBH (i.b.) - (5-yr. increment * 2) = 1969 DBH (i.b.)
5. 1969 DBH (i.b.) * 1.088 = 1969 DBH (O.b.)
6. 1974 DBH (i.b.) - (10-yr. Increment * 2)=1964 DBH (i.b.) :
7. 1964 DBH (i.b.) * 1.088 = 1964 DBH (o.b.) . \
156
-------
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-------
Key to
Tables C3 &C4
Variable
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
Labels
DB70
DB75
DB76
DB77
BA70
BA75
BA76
BA77
V75
V76
V77
D5-0
D7-5
D6-5
B5-0
B7-5
B6-5
V7-5
V6-5
Parameter
DBH 1970
DBH 1975
DBH 1976
DBH 1977
Basal Area 19/0
Basal Area 1975
Basal Area '1976
Basal Area 1977
Volume 1975
Volume 1976
Volume 1977
(DBH75 - DBH70)/5
(DBH77 - DBH75)/3
(DBH76 - DBH75)/2
(BA75 - BA70)/5
(BA77 - BA75)/3
(BA76 - BA75)/2
(Volume 77 - Volume 75)/3
(Volume 76 - V-lume 75)/2
161
-------
Table C-3
Treatment means all trees
Trieaonent: Loy .Level Sludge "| QO
VAR
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
IB
19
LABEL
DB70
DB75
DB76
DB77
BA70
BA75
BA76
BA77
V75
V76
V77
D5-0
B7-5
D6-5
B5-0
B7-5
B6-5
V7-5
M6-5
MEAN
164.9691
178.1649
186.1443
189.3918
0.0242
0.0281
0.0309
0.0321
0.2753
0.3220
0.3363
2.6392
3.7423
3.9897
0.0008
0.0013
0.0014
0.0203
0.0233
STD-DEV
59.2251
63.8735
68.7330
70.7252
0.0215
0.0250
0.0274
0.0283
0.3016
0.3471
0.3564
1.1044
2.8122
2.9747
0.0007
0.0013
0.0014
0.0202
0.0244
MIN
7.6000E 01
8.3000E 01
8.4000E 01
8.4000E 01
5.0000E-03
5.0000E-03
6.0000E-03
6.0000E-03
3.2000E-02
3.4000E-02
3.4000E-02
6.0000E-01
0.
0.
0.
0.
0.
3.3333E-04
5.0000E-04
MAX
4.9000E 02
5.2700E 02
5.4500E 02
5.4800E 02
1.8900E-01
2.1800E-0.1
2.3300E-01
2.3600E-01
2.7030E 00
3.0350E 00
3.0690E 00
7.4000E 00
l.OOOOE 01
1.2000E 01
5.8000E-03
6.0000E-03
7.5000E-03
1.2200E-01
1.6600E-01
Treatment: Low Level Sludge + Water 100W
UAR
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
LABEL
DB70
BB75
BB76
DB77
BA70
BA75
BA76
BA77
V75
V76
V77
D5-0
D7-5
06-5
B5-0
B7-5
B6-5
V7-5
•V6-5
MEAN
155.7451
166.7451
174.3922
177.2941
0.0212
0.0245
0.0272
0.0283
0.2466
0.2898
0.3040
2.2000
3.5163
3.8235
0.0007
0.0012
0.0013
0.0191
0.0216
STD-DEV
53.4202
59.3599
65.8076
68.3580
0.0158
0.0189
0.0221
0.0234
0.2169
0.2690
0.2855
1.2731
3.4133
3.6672
0.0006
0.0016
0.0017
0.0238
0.0269
MIN
9.0000E 01
9.3000E 01
9.4000E 01
9.4000E 01
6.0000E-03
7.0000E-03
7.0000E-03
7.0000E-03
4.6000E-02
4.6000E-02
4.6000E-02
6.0000E-01
0.
0.
0.
0.
0.
-3.3333E-04
-5.0000E-04
MAX
3.0300E 02
3.3100E 02
3.4700E 02
3.5400E 02
7.2000E-02
B.6000E-02
9.5000E-02
9.8000E-02
9.0600E-01
1.1080E 00
1.1430E 00
6.2000E 00
1.2000E 01
1.3000E 01
2.8000E-03
6.3333E-03
6.5000E-03
9.1333E-02
1.0900E-01
Cconf'dl
162
-------
Table C-3 (continued)
Treatment: Mid
VAR
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
LABEL
DB70
DB75
DB76
DB77
BA70
BA75
BA76
BA77
V75
V76
V77
D5-0
07-5
D6-5
B5-0
B7-5
B6-5
V7-.5
V6-5
Level Sludge
MEAN
142.3472
153.7292
160.3750
162.7361
0.0180
0.0213
0.0234
0.0242
0.2029
0.2400
0.2498
2.2764
3.0023
3.3229
0.0006
0.0010
0.0011
0.0156
0.0185
200
STD-DEV
52.7329
59.0864
64.2980
66.1230
0.0135
0.0164
0.0188
0.0196
0.1747
0.2141
0.2241
1.3812
2.6284
2.9313
0.0006
0.0011
0.0012
0.0169
0.0203
MIN
5.2000E 01
5.2000E 01
5.3000E 01
5.3000E 01
2.0000E-03
2.0000E-03
2.0000E-03
2.0000E-03
6.0000E-03
7.0000E-03
7.0000E-03
0.
0.
0.
0.
0.
0.
-3.3333E-04
-5.0000E-04
MAX
2.8300E 02
3.1300E 02
3..3500E 02
3-.4000E 02
6.3000E-02
7.7000E-02
8.8000E-02
9.1000E-02
7.7900E-01
9.6000E-01
9.7000E-01
6.6000E 00
1.0333E 01
1.1OOOE 01
2.8000E-03
4.6667E-03
5.5000E-03
6.3667E-02
9.0500E-02
Treatment: Mid Level Sludae. + Water 200W
IAR
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
LABEL
DB70
DB75
DB76
DB77
BA70
BA75
BA76
BA77
V75
V76
V77
D5-0
D7-5
D6-5
B5-0
B7-5
B6-5
V7-5
V6-5
MEAN
140.750O
151.0294
158.8824
162.6471
0.0184
0.0214
0.0241
0.0253
0.2092
0.2479
0.2633
2.0559
3.8725
3.9265
0.0006
0.0013
0.0013
O.0181
0.0193
STD-DEV
60.1918
67.5700
74.0J46
77.0628
0.0161
0.0194
0.0226
0.0240
0.2141
0.2615
0.2775
1.4842
3.4804
3.5305
0.0007
0.0016
0.0017
0.0221
0.0244
MIN
4.5000E 01
4.5000E 01
4.7000E 01
4.8000E 01
2.0000E-03
2.0000E-03
2.0000E-03
2.0000E-03
6.0000E-03
7.0000E-03
8.0000E-03
0.
0.
0.
0.
0.
0.
3.3333E-04
5.0000E-04
MAX
2.9800E 02
3.2800E 02
3.4600E 02
3.5500E 02
7.0000E-02
8.4000E-02
9.4000E-02
9.9000E-02
9.0000E-01
1.0600E 00
1.1160E 00
6.0000E 00
1.2667E 01
1.3500E 01
2.8000E-03
6.3333E-03
6.5000E-03
0.5000E-02
1.0150E-01
(cbnt'd)
163
-------
Table C-3 (continued)
Treatment: High Level Sludge 300
gflR LABEL
1 DB7O
2
3
4
5
6
7
9
10
11
12
13
15
17
•L /
18
19
DB75 -
DB76
DB77
BA70
BA75
BA76
BA77
V75
V76
V77
D5-0
B7-5
D6-5
B5-0
B7-5
B6-5
V7-5
V6-5
MEAN
161.4957
173.8696
181.4348
184.7565
0.0233
0.0271
0.0297
0.0308
0.2640
0.3101
0.3246
2.4748
3.6290
3.7826
0.0007
0.0013
0.0013
0.0202
0.0230
STB-BEV
60.3884
65.1306
70.1706
72.0171
0.0181
0.0212
0.0238
0.0248
0.2319
0.2783
0.2896
1.0821
2.6618
2.8478
0.0006
0.0013
O.0014
0.0202
0.0236
MIN
7.3000E 01
7.9000E 01
8.1000E 01
8.4000E 01
4.0000E-03
5.0000E-03
5.0000E-03
6.0000E-03
3.2000E-02
3.3000E-02
3.7000E-02
4.0000E-01
0.
0.
0.
0.
0.
0.
0.
MAX
3.3400E 02
3.6000E 02
•3.7900E 02
3.8500E 02
8.8000E-02
1.0200E-01
1.1300E-01
1.1600E-01
1.1170E OO
1.3160E 00
1.3070E 00
6.0000E 00
9.3333E 00
1.0500E 01
3 . 2000E-03
5.3333E-03
6.0000E-03
8 . 4333E-02
I.OIOOE-OI
Treatment: Ettgh.
VfiR
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
LABEL
DB70
BB75
BB76
DB77
BA70
BA75
BA76
BA77
V75
V76
V77
B5-0
B7-5
B6-5
B5-0
B7-5
B6-5
V7-5
V6-5
Level Sludge +
MEAN
159.3559
170.2373
177.6949
181.5763
0.0222
0.0256
0.0282
0.0296
0.2522
0.2964
0.3132
2.1763
3.7797
3.7288
0.0007
O.0013
O.0013
0.0203
0.0221
Witer 300W
STD-DEV
54.9259
60.8810
66.5959
69.5352
0.0147
0.0175
0.0200
0.0215
0.1903
0.2331
0.2496
1.2172
3.2149
3,1980
0.0006
0.0014
O.0014
0.0207
0.0221
MIN
6.7000E 01
6.8000E 01
6.8000E 01
7.0000E 01
4.0000E-03
4.0000E-03
4.0000E-03
4.0000E-03
2.3000E-O2
2.3000E-02
2.5000E-02
2.0000E-01
0.
0.
0.
0.
0.
0.
0.
MAX
2.8100E 02
3.0500E 02
3.2200E 02
3.2800E O2
6.2000E--02
7.3000E-02
8 . 1OOOE-02
8 . 4000E-02
7.6300E--01
8.9500E--01
9.5400E-01
4.8000E 00
1.0333E 01
1.0500E 01
2.2000E-O3
4.6667E-03
4.5000E-03
7.3000E-02
7.7500E-02
(cont'd)
164
-------
Table C-3
Treatment: Hater only
VAR
1
2
3
4
» 5
6
7
8
9
16
11
12
13
14
15
16
17
18
'19
LABEL
DB70
DB75
DB76
DB77
BA76
BA75
BA76
BA77
V75
V76
V77 -
D5-6
D7-5
B6-5
B5-6
B7-5
B6-5
V7-5
V6-5
MEAN
180.1042
192.9583
200.5313
203.5729
0.0292
0.6334
6.0363
0.0376
0.3381
0.3958
0.4120
2.5708
3.5382
3.7865
0.0008
0.0014
0.0015
0.0246
0.0289
TreaBBent; Vnirrigated .control
.VAR
1
2
3
4
5
6
7
8
9
16
11
12
13
14
15
16
17
18
19
LABEL
BB70
BB75
DB76
DB77
BA70
BA75
BA76
BA?7
V75
V76
V77
B5-0
D7-5
D6-5
B5-0
B7-5
B6-5
V7-5
V6-5
MEAN
203.0789
216.6579
224.5526
228.7632
0.0348
0.0400
0.0432
0.0450
0,4675
0.4633
6.4848
2.7158
4.6351
3.9474
6.0010
0.0017
0.0016
0.0258
O.0279
STD-BEU
69.0003
72.9698
78.1973
80,7160
O.0226
0.6254
6.6281
6.6295
6.2807
0.3322
O.3503
0.9629
2,9635
3.0015
0.0006
0.6615
6.6015
0.6243
6.6269
STD-DEV
58.0644
63.8928
68.6226
71.1414
0.0187
0.0221
0.0246
0.0260
O.2391
0.2787
0.2968
1.3296
2.7188
2.7773
0.0007
0.0014
0.0014
0.0200
0.0209
MIN
5.3000E 01
5.6060E 01
5.7000E 01
5.70.00E 01
2.0000E-03
2.0606E-63
3.6600E-03
3.0000E-03
l.OOOOE-02
l.OOOOE-02
l.OOOOE-02
6.0000E-01
0.
0.
0.
0.
0.
-6.6667E-04
-l.OOOOE-03
MIN
1.0700E 02
1.1200E 02
1.1200E 02
1.1300E 62
9.6000E-03
l.OOOOE-02
l.OOOOE-62
1.6000E-02
8.4000E-02
8.6000E-02
8.8000E-02
6.0000E-01
3.3333E-01
0.
2.0000E-04
0.
0.
1.3333E-03
l.OOOOE-03
MAX
3.8300E 02
4.0300E 02
4.2100E 02
4.3000E 02
1.1500E-01
1.2800E-01
1.3900E-01
1.4500E-01
1.3600E 00
1.5620E 00
1.6860E 00
5.6000E 00
1.0333E 01
1.1000E 01
3.0000E-03
5.6667E-03
5.5000E-03
1.0867E-01
1.0100E-01
MAX
3.O900E 02
3.3400E 02
3.4800E 02
3.5600E 02
7.5000E-02
S.8000E-02
9.5000E-02
l.OOOOE-01
9.2000E-01
1.0400E OO
1.0960E 00
5.0000E 00
9.3333E 00
9.5000E 00
2.6000E-03
4.6667E-03
4.5000E-03
6.9000E-02
7.0500E-02
(cont'd)
165
-------
Table C-4
Treatment means paired trees
Treatment: Low Level Sludge 100
•VAR L
I
_ 2 _
4
5
— 6 ' '
7' '
3"
10-
11
—12 '
13
14
16
17
"IIT
19
ABEL ' '
D870 IE
D875 2(
•DB76 " ~2I
Da 77 21
BA70
" BA75
BA76
BA77
-V75
V76
V77
05-0 '
D7-5
06-5
B5-0
S7-5
65-5
V7V5 -
VS-5
' ffiEAN .
I6.6OOO
XD.6236__
512571
0.0296
•O':03'44~
0.0382
0.0399
ol40l7
0.4233
2.8057"
4.8762
5.1571
-OTTO 1 CT-
0.0018
0.0019
Olo3l4
STD-DEV MIN
53.8796 8.4000E 01
59.1136 9.1000E 01
6477597 973iJOOE~U 1 —
67.1015 9.6000E 01
0.0158 6.0000E-03
OBOIST 7IOOOOE-03 ~
0.0214 7.0000E-03
0.0228 7.0000E-03
0.2039
O.2434
0.2622
U3271
2.9485
3.1872
' "" 0.0006
0.0014
0.0015
~- 0.0204
0.0233
4.200OE-02
4. 6 OOOE-02
5.1 OOOE-02
6.OOOOE-01"-
3.3333E-OI
5.0000E-01
a. " *
0.
-o.
1 . 6667E-03 ~
2.0000E-03
MAX
2.78001- 02
3.0300E 02
"3;'2200E"02
3.2900E 02
6 . 1 OOOE-02
B'.\ OOOE-02
8.5000E-02
el8400E-0!
9.1500E-01
•s.-oocorroo
l.OOOOE 01
1.2000E 01
4i6667lil-03
5.5000E-03
7.I333E-02
9.1500E-02
Treatment: Low Level Sludge + Water 1QQW
VAR
1
2
3
4
5
6
7
a
9
10
ii
12
13
14
15
16
17
18
19
LABEL
DB70
DB75
DB76
DB77
BA70
8A75
8A76
3A77
V75
V76
V77
D5-0
D7-5
D6-5
B5-O
B7-5
B6-5
V7-5
V6-5
MEAN
"170.6296
182.5926
IP2.2963
195.7037
O.O259
0.0301
0.0337
O.03SO
0.3107
0.3703
0.3872
2.3926
4.3704
4 .8S 1 9
o.ooos
0.0016
O.0018
0.02S5
0.0298
STO-DEV •
44.1112
70.9617
78.0320
80.8564
0.0195
0.0231
.. 0--fj277j
0.0284
0.2661
"0.'3283'
0.3460
1.4342
•— 3;<5519~"
3.8676
0.0007
' "*b.OOI9""
0.0021
0.0274
1)'. 0319""
MIN
9.0000E 01
9.3000E 01
9.4000E 01
9.4000E 01
6.0000E-03
7.0000E-03
~7:0000"E-03
7.0000E-03
4.6000E-02
4.6000E-02
4. 6 OOOE-02
6.0000EHD1
~3: 533312-01
5.0000E-01
0.
"0."
0.
0.
"o. ' •
MAX
3.0300H 02
3.3100E 02
3.4700E: Oz
3.5400E 02
7.2000K-02
8.6000E-02
9.5000EE-02
9.3000H-02
9.0600E-JI
1.1 OBOE 00
1.14301= 00
5.6000(1: OJ
1. 20601s 01
1. 3000(~ 01
2.8000H-03
6.3333E-03
6.5000E-03
9.1333E-02
l."0900E-Oi
tcont'd)
166
-------
Table C-4 (continued)
Treatment: Mid Level Sludge 200
1
2
'3
4
5-
6
7
8
-•-9
1O
_11
12
13
14
"15
16
17
IS
19
LABEL
DB70
DB75
•' ' DB76
- . DB77
BA70
8A75"
SA76
BA77
"V75 "
V76
V77
D5-6
D7-5
D6-5
• B5-0"
S7-5
B6-5
" "" V7-5" "
V6-5
MEAN .
170.7568
184.2973
STD-DEV
48.1805
54.3455
9.0000E 01
9.4000E 01
T95T1081 5'9I"4730 •~9r6000E~01
198.4324
0.0246
61.6079
0.0125
9.6000E 01
6. OOOOE-03
TO". 0289 0 . Q 1 5 1 7 . OOOOE-03
0.0326
0.0338
-"0.-2843
0.3440
0.3586
2"T7bST
4.7117
5.4054
~"'0i'0009'
0.0016
_ P_«opJ_8
0.0248
0.0299
0.0176
O.OJ34
"' 0.1617 -
0.2016
0.2119
"~T.343S~~
2.7724
2.9717
— o;ooo6
0.0012
0.0013,..
O.01 73
0.0208
7. OOOOE-03
7. OOOOE-03
'4;9000E-02
5.3000E-02
5.3000E-02
6.obodir-of
3.3333E-01
5.0000E-01
or -••-
0.
.0.
6. 6667E— 04
1 .OOOOE-03
MAX
2.5400E 02
2.7500E 02
T~2".9200E '02
. 2.9500E 02
5 . 1 OOOE-02
5.9000E-02
6. 7 OOOE-02
6.8000E-02
5;7700E-OI
7.0600E-OI
7.3100E-01
S.OOOOE'OO"
1.0333E 01
I.IOOOE 01
" 1.8000E-0'3'
4. OOOOE-03
4.5000E-03
5~.9333E-02~"
6.9500E-02
Treatment: Mtd Level Sludge + Water
VAR
—_....
2
3
A
6
6
" 7
8
9
"10
II
12
13
14
_I5
17
18
LABEL
" DB70~
DB75
DB76
DB77
8A70
BA75
BA76
BA77
V75
V77
05-O
D7-5
Q6-5
85-0
67-5
B6-5 .
V7-5
Vtf-5
MgAl-l
. .T63S"
1 66. S8&S>
175.9259
180.1052
O.C203
O.O243
0.0274
0.0239
0.238S
""0.2835
0.3030
2.3852
""4.4321
4.5135
0.0007
O.00I6
0.0215
0.0225
er 200W
STD-UI-:V
"50. "88 4!
57.1081
63.9945
67.3853
0.0132
0.0160
O.OI91
0.0206
O. 1 746
0.2189 ~
0.2391
1 .2501
3.6219
3.6387
_ 0 . 0006
0.001 6
0.001^
0.0223
0.0228
MIN
8.6000E 01
8.9000E 01
9.0000E 01
9.0000E 01
6. OOOOE-03
6. OOOOE-03
6"; OOOOE-03
6.0000E-03
4 s 4 pOtfE™ 02
~4.7dddE-02'
4.7000^-02
6.0000E-OI
" 3 i 3333E— 0 1
0.
0.
"o"
O.
1 . OOOOE-03
5'J OOOOE-0'4
MAX
2.5300E 02
2.7700E 02
2.0400E OZ
3.1500E O2
5 . OOOOE--02
. 6.00OOE-02
7.3000E-02
7.8OOM.-01
,_,6,4IOOE-01
•8.1700E-01
8.7500E-01
4.8000£ 00
" " I.2667E 01
1.3500E 01
2. OOOOE-03
6.0OQQB-Q3
6.SOOOE-03
7.8000H-02
8 '.3 OOOE-02
(cont^d)
167
-------
Table C-4 (continued)
_Tre*tment: High Level Sludge 300
VAR
1
— 2
3
4
1 b
6-
7
• - 8
9
10
- IT '
12
13
14
15
16
17
19
IP
LABEL MEAN
DB70 .193.2973
DB75 '" "20678649
DB76 217.0811
DB77 221.4324
• BA/0
BA75
BA76
8A77T
V75
V76
V77 '
05-0
D7-5
D6-5 ••-"
B5-0
B7-5
- ' B6-5
V7-5
V6-5
0.0 J24
0.0374
'0.0415
-0.0432 —
0.3779
0.4458
2.7135
4.8559
- 5.1 Oar -
0.0010
0.0019
070020 —
0.0305
0.0340
STD-DEV
64.4601
7079570"-
76.2647
77.9550
" O.OT9b
0.0230
0.0259
— 0.0269 "
0.2508
0.3010
1.3321
2.6811
2.9654
O.0007
O.0014
0:0015' "
0.0227
0.0257
MIN
8.1000E 01
874000E"01-'
a.5000E 01
6.500QE Ol
-570-OOOE-OT-
6.0000E-03
6.OOOOE-03
6:OOOOE-03"
3.8000E-02
3.SOpOE-02_
6loOOOE-oT
3.3333E-OI
SiOOOOE-Ol"
2.0000E-04
0.
u.
0.
0.
MAX
3.0IOOE 02
"3.-2500E 02
3.4200E 02
3.4700E 02
~77i'0'OOEE-02
8.3000E--02
9.2000IE-02
- -9/5000E-02
8.7400I:-01
1.0340!- 00
~~170530E" 00
5.0000E 00
8.6667E 'X)
— 9.5000E 00
2.4000E-03
4.6667E-03
5.0000E-03
8.4333E-02
8.6000E-02
Treatment: High Level Sludge •»• Water . 300W
VAR LABEL
- '1 •--•DB70"
2 DB75
3 DB76
4 -DS77-
5 3A70
6 BA75
-7—
8
9
- 10
II
12
-"13"
14
15
• 16
17
13
"19
BA76
BA77
V75
V76--
V77
U5-0
D7-5~
D6-5
85-0
87-5-
B6-5
V7-5
-••V6=5"
MEAN • STD-DEV
"• 182 '.4848 53"."714"6
195.6061 59.9348
2O5.0606 66.2471
— 2 1 0. 0606— 69 .-222O-
0.0233 0.0157
0.0328 0.01Q7
u.Ojoo
0.0382
0.3294
-OJ3899
0.4133
2.6242
4.7273
0.0009
0.0018
0.0017
0.0230
10. 030 J
0.0232
0.2054
0.2526
0.2707
1 .2764
3--A rtft 1
.499 1
3.5446
0. 0006
0.0016
0.0016
0.0232
O.O245
... **I!!
9*3000E 01
9.4000E 01
• 9r4000ET 01 -
6.0000E-03
7.0000E-03
7.0000E-03
5.3000E-02
•5.'5000E"-02"
5.5000E-02
6.0000E-01_
0.
2.0000E-04
0.'
0.
6.6667E-O4
MAX
""2~.8ldOiE"b2'
3.05aiE 02
3.220CIE 02
— 3:2800E 02"
6.2000E-02
7.3_OOpE-02
8.4000E-02
7.6300n-01
— 8.-9500E-01
9.5400E-01
4.SOOOE 00
~"r.0333E 01
1.0503E 01
2.200DK-03
— 4.6667E-03
•4.5000E-03
7.3000E-02
7;75flOE-02
(cont'd)
168
-------
Table C-4 (continued)
_Treatment: Water only
TAR 1
1
2
3
4-
5-
• 6"
7-
fi
.. . „ ...
10
11
' 12
• 13
14
~15
16
17
-18 '
1?
.ABEL
DB7J
DB75
DB73
DB77
BA7J
BA75
BA76
BA77
' V7V
V76
V77
D5-0
D7-5
D6-5
•B5-0
B7-5
B6-5
"V7-5
V6-5
MEAN " STD-DEV^
192.5185 62.0089
203.3704 67.3790
215.2222 72.4565
213.6667 74.5773
0.0320 0.0135
" * 0.0370
0.0404
0.0418
0.3764
0.4447
0.4600
2i7704
4.09S8
4.4259
OT0010"
0.0016
O.OOI7
0.0279
0.0341
0.0216
O.0240
0.0251
O.2399
0-.237S
0.2935
•-. i;i39j
2.7S55
2.8730
OT0065-
0.0013
0 . 00 1 4
0.0210
0.0253
MIN •
8.7OOOE 01
9.30006 01
9.4000E 01
9.4000E 01
6.OOOOG-03
7rOGOOE-03"
7.0000E-03
7.0000E-03
4.50QOE-02
4.4000E-02
4.4000E-02
'6.0000001'
3.3333E-01
0.
'o.'
0.
o.
-6.66fi7E-04'
- 1 : OOOOE-O3
•* ' MAX'
2.9700E 02
3.1900E 02
3.2900g 02
.3.300O6 02
6.9003E-02
'~"8;OOOOE-02
8.5000E-02
8.60OOE-02
8.4500E-JI
9.5500E-01
9.6100E-OI
".si'ooooe oo
3.66o7R 00
8.50QOE 00
2720005-03"
4.0000E-03
4.00GOE-03
"' 7; OOOOE-02
7.9500E-02
Treatment: tJnirrigated control
VAR
i
a
3
4
5
"6
7
8
" 9
10
.. U
12
13
14
15
16
17
""18
19
"LABEL"
DB70
DB75
DB76
DB77
BA70
BA75
BA76
BA77
V75
V76
V?7_
05-0
D7-S
D6-5
B5-0
B7-5
B6-5
V7-5
V6-5
ilEAH
205.6757
219.2162
227.1392"
231.4595
0.0355
O.0408
0.0440
0.0459
".""" o:4i58 """"
0.4727
Q ,.494.6. _„
2. 7081
4.081 1
3.9865
0.0010" ~
0.0017
0.0016
0.0263
0.0285
STD-DEV
56.5843
.62,7699
67.5893
70.1267
0*018.4...
0.0219
0.0244
0.0258
"5:2368
0.2764
_fl, 29.4.6 _
1.3471
2.7413
2.8050
0.0007
0.0014
0.0014
0.02OO
0.0209
MIN
1.0900E 02
U120QE.Q2
J.1200E 02
1.1300E 02
2i_09QQE^.Q3.-
1 . OOOOE-02
1. OOOOE-02
I.OOOOE-g2
8:4ddOE-d2
8.6000E-02
8.aQQOE=.0.2_
6. OOOOE-0 1
3.3333E-01
0.
2.0000E-04'
0.
0 • —
t . 3333E-03
1 . OOOOE-03
MAX
3.0900E 02
._3.3400E 02
3.4300E 02
3.5600E 02.
7 1 5000Ejr02
8.8OOOE-02
9.5000E-02
1 . OOOOE-0 1
"9I2000E-01
1 .0400E 00
l..09<50E .00
5.0000E 00
9.3333E 00
9.5000E 00
2.6000E-03
4.6667E-03
485000E-03
6.9000E-02
7.0500E-02
- ' (cont'd)
169
-------
TECHNICAL REPORT DATA .
(Please read Instructions on the reverse before completing)
REPORT NO.
PA-600/2-80-002
3. RECIPIENT'S ACCESSION-NO.
. TITLE AND SUBTITLE
EFFECTS OF SLUDGE IRRIGATION ON THREE PACIFIC
NORTHWEST FOREST SOILS
5. REPORT DATE
March 1980 (Issuing Date)
6. PERFORMING OF1GANIZATION CODE
. AUTHOR(S)
8. PERFORMING ORG/
David D. Wooldridge and John D. Stednick
. PERFORMING ORGANIZATION NAME AND ADDRESS
Municipality of Metropolitan Seattle
Exchange Building, 821 Second Avenue
Seattle, Washington 98104
10. PROGRAM ELEMENT NO.
1BC821, SOS #1, Task C/09
11. CONTRACT/GRANT NO.
R-802172-03
2. SPONSORING AGENCY NAME AND ADDRESS
Municipal Environmental Research Laboratory--Cin.,OH
Office of Research and Development
U.S. Environmental Protection Agency
Cincinnati, Ohio 45268
13. TYPE OF REPORT AND PERIOD COVERED
14. SPONSORING AGENCY CODE
EPA/600/14
^.SUPPLEMENTARY NOTES
•reject Officer: Gerald Stern (513) 684-7654
6. ABSTRACT
A sprinkler irrigation system developed for uniform applications of anerobically
digested, municipal-industrial sewage sludge initially applied up to 5.8 mt/ha/wk,
Reduced infiltration of sludge occurred due to physically blocking of soil pores,
causing ponding of sludge in the micro-depressions. Sludge loading rates were
decreased to 10, 20, 30 and 40 mt/ha/yr. .......
The renovating capactiy of forest soils for most suspended and dissolved constitu-
ents in sludge was very good (95 to 99+%). Nitrogen was the exception as nitrification1
rates increased with increased rates of sludge applications, resulting in leaching of
NOs-N and concomitant cation losses in soil wa ter through the surface 2 m of soil.
Leaching losses did not alter dissolved ions in ground water at 10 m. Phosphorus in
all forms was never found in significant amounts in soil solutions of tested soils.
Optimum loading rates of 20 to 30 mt/ha/hr. of sludge show trends to increased
surface soil total N, organic material and cation exchange capacity.
Analyses for virus at all depths in the soil and from the soil solution at
corresponding depths were negative, nor were human pathogens of the bacteria type
isolated from the limited numbers of soils and soil solutions analyzed.
Sludge applications increased the growth rate of treated trees. Water applied
after sludge irrigation also may enhance tree growth over sludge only applications.
KEY WORDS AND DOCUMENT ANALYSIS
DESCRIPTORS
b.lDENTlFIERS/OPEN ENDED TERMS
:. COSATI field/Group
Sludge, Sludge disposal, Waste disposal,
Forestry, Forest land, Trees (plants),
Soils, Soil analysis, Soil chemistry,
Irrigation, Sprinkler irrigation, Surface
irrigation
13B
18. DISTRIBUTION STATEMENT
Release to Public
19. SECURITY CLASS (ThisReport)'
Unclassified
21. NO. OF PAGES
184
20. SECURITY CLASS (Thispage)
Unclassified
22. PRICE
EPA Form 2220-1 (9-73)
170
* U.S. GOVERNMENT PRINTING OFFICE: 1980 -657-146/5646
-------
-------
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