G R O U N D W A T E R A N D S U R F A C E WATER
C O N T A M I N A T I O N BY
RETARDANTS AT ABBOTSFORD
AIRPORT
by
CINDY
L. O T T
A THESIS SUBMITTED IN PARTIAL F U L F I L M E N T
T H E REQUIREMENTS
FOR T H E DEGREE
MASTER O F
OF
SCIENCE
in
T H E F A C U L T Y O F G R A D U A T E STUDIES
INTERDISCIPLINARY
STUDIES
We accept this thesis as conforming
to the required standard
T H E UNTVTSRSITY^OF BRITISH C O L U M B I A
JULY,
®
CINDY
L
1985
OTT,
1985
OF
FIRE
In p r e s e n t i n g t h i s t h e s i s i n p a r t i a l f u l f i l m e n t of the
r e q u i r e m e n t s f o r an advanced degree a t t h e U n i v e r s i t y
o f B r i t i s h C o l u m b i a , I agree t h a t t h e L i b r a r y s h a l l make
i t f r e e l y a v a i l a b l e f o r r e f e r e n c e and s t u d y . I f u r t h e r
agree t h a t p e r m i s s i o n f o r e x t e n s i v e c o p y i n g o f t h i s t h e s i s
f o r s c h o l a r l y purposes may be g r a n t e d by t h e head o f my
department o r by h i s o r h e r r e p r e s e n t a t i v e s .
It is
understood that copying or p u b l i c a t i o n of t h i s t h e s i s
f o r f i n a n c i a l g a i n s h a l l n o t be a l l o w e d w i t h o u t my w r i t t e n
permission.
Department o f
The U n i v e r s i t y o f B r i t i s h Columbia
1956 M a i n
Mall
Van couve r , Canada
V6T
1Y3
Date
t
JiJffijnJto.
I(n
}
ftKS
ii
Abstract
The
impact of fire retardant waste on the aquatic environment was investigated
at Abbotsford
Airport located in the Lower Fraser Valley, in Southwestern British
Columbia. The
cleaning of fire fighting aircraft results in significant quanitities of fire
retardant waste being washed into the airport drainage system with subsequent transport
to a drainage ditch located in the southwest corner of the Airport Chemical
components of the fire retardant likely to be of environmental
concern were identified
as ammonia, phosphate, and a corrosion inhibitor.
Glacial and outwash deposit? consisting of sands and
gravels comprise the
surficial geology of the study area. Hence, the fire retardant waste would have the
potential to impact both surface watt: and groundwater resources. Therefore
concern due
and
was
to the extensive use of groundwater in the local area for both drinking
irrational purposes.
The
and
there
major components of the research design were 1) assessment of the spatial
temporal distribution of fire retardant introduced into the aquatic environment, and
2) overall impact of fixe retardant contamination
on surface water and
groundwater
quality.
A
long term and
two short term monitoring programs were designed to
determine the rate of transport and
distribution of the fixe retardant in the aquatic
environment Results showed that although
the fire retardant was
observed to wash
through the drainage system into the stream, no measuxable impact on surface watex
quality was
recorded
during the study- period. Fixe xetardant components which would
cause surface water contamination
are ammonia, phosphorus, iron and chromium. A
significant rise in nitrate-nitrogen concentration was
less than a day after fire retardant waste was
detected in groundwater samples
recorded in measurable quanitities in
the ditch water. Temporal distribution of fire retardant in the aquatic environment
correlated with the high hydraulic conductivity of the subsurface and
ii
specific
was
hydrological events involving heavy precipitation. Results from the laboratory column
experiments indicated that components of the Fire retardant were not retained in the
soil and would therefore be rapidly leached into groundwater.
Surface water quality and groundwater quality results were compared with
established water quality standards for drinking water and protection of freshwater
aquatic life. On
the basis of these standards the fire retardant waste was not found to
contribute to degradation of the surface and groundwaters at Abbotsford Airport
Overall impact of the fire retardant waste on the aquatic environment at
Abbotsioid Airport during the study period was not found to be significant The low
fire season combined
with a change in washing policy resulted in a fewer number of
planes being cleaned at Abbotsford Airport during 1983-84. Therefore, the impact on
the
aquatic environment recorded during this period cannot be considered typical.
iii
iv
Table of Contents
Abstract
ii
Table of Contents
iv
List of Tables
vii
List of Figures
viii
Acknowledgements
~x
1.
INTRODUCTION
.„
1
2.
B A C K G R O U N D A N D I J T E R A T U R E REVIEW
5
2.1 Introduction to Hre Retardants and Their Use
5
12 Nitrogen Component
?
2.3 Phosphorus Component
2.4 Corrosion Inhibitor
2.5 Colorant
3.
„
19
,
21
METHODS
3.1 Sampling Design
22
.
_
22
3.1.1 Sampling Design"- Field Work
...22
3.1.1.1 Field Locations
22
3.1.1.2 Frequency
24
3.1.1.3 Parameters Measured
27
3.1.2 Drilling Program to Install Piezometers
27
3.1.3 Laboratory Experiment
30
3.1.3.1 Materials
30
3.1.3.2 Procedure
30
3.1.3.3 Sampling Design
~
30
3.2 Sampling Procedures
32
3.3 Chemical Analysis
33
3.3.1 Water Samples
33
V
3.3.2 Soil and Sediment Samples
34
3.4 Hydraulic Conductivity
34
3.5
Statistical Analysis
35
3.5.1 Overview
35
3.5.2 Mann-Whitney
U
Test
35
3.5.3 Trend Analysis
37
3.5.4 Correlation
_
37
3.5.5 Multivariante Cluster Analysis .—
3.6 Water Data
4.
.
DESCRIPTION O F
THE
38
STUDY AREA
39
4.1 General Description
39
4.2 Surficiii Geology
39
4.3
5.
37
Groundwater Hydrology
_
43
4.3.1 Groundwater Flow
43
4.3.2 Groundwater Chemistry
51
4.4 Climatic Influence on Hydrology
53
4.5
58
Land Use
RESULTS A N D
DISCUSSION
60
5.1 Assessment of Water Data
60
5.1.1 Introduction
60
5.1.2 Ditch water
63
5.1.3 Stream Water
:
67
5.1.4 Groundwater
74
5.1.5 Multivariante Cluster Analysis
82
5.2 Relationships Between Water and Pollutant
83
5.2.1 Background Relationships
84
5.2.2 Peak Row
85
Conditions
vi
5.2.3 Multivariante Cluster Analysis
6.
89
5.3 Column experiment
90
5.4 Ditch Sediment
93
5.5 Summary
94
M A N A G E M E N T IMPLICATIONS
96
6.1 Introduction
.'.
96
6.2 Legislative Framework
-
6.3 Administrative Framework
98
6.4 Water Quality Standards
6.5 Summary - Management Implications
7.
CONCLUSIONS A N D
96
102
_
107
RECOMMENDATIONS
108
7.1 Conclusions
108
7.2 Recommendations
110
REFERENCES
I l l
A P P E N D I X A - USE OF C H E M I C A L FIRE R E T A R D ANTS IN CANAJJ
117
APPENDIX B - SUBSURFACE DATA
119
APPENDIX C - W A T E R Q U A L I T Y D A T A
126
A P P E N D I X D - C A N A D I A N E N V I R O N M E N T A L LEGISLATION
:
129
APPENDIX E - FIELD STUDY C H E M I C A L DATA
-131
APPENDIX F - LABORATORY STUDY C H E M I C A L DATA
136
vii
List of Tables
Table
2.1 Description of PhosChek
PAGE
XB
7
2.2 Temperature Related K.^ Values
12
2.3 Potential Ammonia in Various Fire Retardants
.13
2.4 P Sorption Capacities of Soils
19
2.5 Toxicity of Corrosion Inhibitors
20
4.1 Regional Row Data
48
4.2 Piezometer Flow Data
51
4.3 Abbotsford Airport Climate Data
S3
5.1 Chemical Data of PhosChek
60
XB
5.2 Aircraft Washing Operations
5.3 Chemical Data of Ditch Water
61
.
63
5.4 Impact of Washing on Ditch Water
64
5.5 Stream Water Chemistry Peaks
67
5.6 Downstream Peaks
67
5.7 Components of Groundwater Clusters
83
5.8 Components of A l l Data Clusters
89
5.9 Chemical Data of Soil in Columns
92
5.10 Chemical Data of Ditch Sediments
94
6.1 Maximum Water Quality Results and Guidelines
103
viii
List of Figures
Figure
PAGE
1.1
Research Framework
2.1
Agricultural Nitrogen Cycle
2.2
Row
2.3
Toxicity of ammonia to fish
15
2.4
Phosphorus Interactions in Soil
16
2.5
Soil pH
IS
3.1
Flowchart of Sampling Design
3.2
Piezometer Nest Locations and Groundwater
3.3
Sampling Locations
26
3.4
Piezometer Nest Construction
29
3.5
Column Set Up
31
3.6
Statistical Design
4.1
Location of Study Area
40
4.2
Surficial Geology of Study Area
41
4.3
Location of Geological Cross Sections
4.4
Geological Cross Section A-A'
45
4.5
Geological Cross Section B-B'
46
4.6
Geological Cross Section C - C
47
4.7
Regional Groundwater
49
4.8
Local Groundwater
4.9
Average Monthly Water Table Level at Abbotsford Airport
Diagram
'.
4
8
of Nitrate and Amino Acid Conversion
11
and Phosphorus Reactions
23
Flow Direction
25
'.
36
_
Flow Direction
Flow Direction
44
50
55
4.10 Daily Precipitation at Abbotsford Airport (August, 1983 to January, 1984)
56
4.11 Winter Storm Scenario
57
4.12 Land Use in the Study Area
59
5.1
Daily Precipitation at Abbotsford Airport (August, 1983 to January, 1984)
Compared with Event and Sampling Dates
62
ix
5.2
Hourly Precipitation During First Storm Event
65
5.3
Nitrogen
66
5.4
Nitrate-Nitrogen Trend in Stream Water
69
5.5
Ammonium-Nitrogen
70
5.6
Phosphorus Trend in Stream Water
5.7
Hourly Precipitation - November 14-16, 1983
5.8
Nitrogen
5.9
Nitrate-Nitrogen Trend Daring November Storm
and Phosphorus Levels During First Storm Event
Trend in Stream Water
_
71
_
and Phosphorus Levels During November Storm
72
73
76
5.10 Nitrate-Nitrogen Spacial Trend in Groundwater
77
5.11 Ammonium-Nitrogen
78
Spacial Trend in Groundwater
5.12 Ortho-phosphate Spacial Trend in Groundwater
79
5.13 Potassium Spacial Trend in Groundwater
SO
5.14 Nitrate-Nitrogen Trend in Groundwater
81
5.15 Nitrogen Trend in Ditch and Groundwater
87
5.16 Rate of Transport in Soil Column
91
6.1
99
Water Quality Control
ix
X
Acknowledgements
This thesis would not have been possible without the help of many people. I
would first like to thank my thesis supervisor, Dr. Hans Schreier, for his advice,
assistance, financial support and endless perseverance
during my research.
I would also like to thank Mr. Hugh Liebscher for his advice and assistance
in the area of hydrogeology
and especially for his help during the drilling program.
Thanks also to Dr. K.en Hall for his advice and loan of equipment during the field
season.
The
staff at Abbotsford Airport helped mai«> my field work very enjoyable.
Special thanks to Jim Logan for providing easy access to the airport property and
information and to Vein and the maintenence crew who never tired of helping me fix
equipment I would also like to thank Bob Sisler of Transport Canada for the
financial support that was given for my field work.
I am also very grateful to Bemie Von Spinder and TD. Nguyen for all the
help and advice while analyzing samples. Also, thanks to Evelyn Wooley who assisted
in sample analysis during a period of heavy sampling.
Dave Ellis of Environment Canada provided excellent background information on
fire retardants and bioassay results.
I am also grateful to Kerry Enns for her time and talent in drawing the
maps and some figures for my thesis.
Last but not least, I would like to thank my friends and family for their
interest and support during the entire time spend finishing my thesis.
x
Chapter 1
INTRODUCTION
Fire retardants are used throughout the summer months in fighting fires in
British Columbia. At the end of the fire season the aircraft used in fighting forest
fires return to Abbotsford Airport for maintenance and cleaning. During the operation
of cleaning the planes, significant quantities of the fire retardant waste collects in the
drainage system and is deposited in the drainage ditch at the southwest comer of the
Airport where it can make its way into nearby streams and groundwater aquifers. Fire
retardants contain several components that could cause water quality problems. The fire
retardant being disposed, Phos-Chek XB, is composed of an ammonium ion, a
phosphate ion, a corrosion inhibitor and a colorant
In the winter of 1982, fisheries officers inspecting Fishtrap Creek noticed that
the ditch entering the creek from the Airport contained a red liquid suL.ta.ice. A n
analysis performed by Inland Waters Directorate on the ditch water at the Airport
indicated high levels of phosphorus, chromium and ammonia. A bioassay performed by
the Department of Fisheries showed this water to be acutely toxic to trout with an
LTJO of between 24 and 48 hours in a 96 hour exposure test
There are two major areas of concern regarding water contamination at the
Airport The first concern is the groundwater. The area of Abbotsford Airport overlies
a major groundwater divide for the underlying aquifer. The surficial materials at the
Airport are glacial outwash deposits consisting mainly of sands and gravels and as a
result the soils are very permeable, therefore, direct infiltration of the contaminants
into the groundwater is predicted. This aquifer is a major source of drinking and
irrigational water in the area.
The other area of concern is the potential contamination of Fishtrap Creek.
The ditch draining the Airport area feeds directly into Fishtrap Creek which crosses
the International Boundary into the United States and drains into the Nooksak River,
1
2
which is a salmon spawning
The
river.
aim of this study was to investigate whether or not the fire retardants are
causing a pollution problem, and if so, to document the extent and the effect of the
pollution on the groundwater and freshwater in the area. The
institutional framework
of the control of this type of pollution was also studied to gain an understanding of
the
management of the pollution at the Airport.
The
four main objectives of this study were:
1.
To determine the type of contamination.
2.
To determine the distribution of contamination with respect to space and time.
3.
To investigate the effect of contamination with regards to various water uses.
4.
To determine the jurisdictional and institutional arrangement
in the control and
regulation of this type of pollution.
The
type of contamination was determined by analysing the fire retardant for
its major components. Also, interactions and transformations of the components in the
various environments were investigated. Critical parameters were determined in order to
monitor the magnitude
The
and extent of the contamination in the hydrological system.
hydrogeoiogy of the Abbotsford Airport region was investigated to
determine the local and regional groundwater
flow directions and flow rates in order
to establish the pollutant flow direction. The
stratigraphy of the region was
determined
to gain an understanding of the potential impact of the infiltration of fire retardant
waste on the groundwater.
The
distribution of the components was determined in the system both spatially
and temporally in order to assess the impact of the contamination. The spatial
distribution of the parameters was monitored in the groundwater in the area
downgradient from the ditch. In Fishtxap Creek, the stream was monitored above and
below the point the ditch entered the stream. The
temporal distribution of the
parameters was detemined by long term monitoring of the stream water, ditch water
3
and groundwater from August, 1983 to March, 1984. In order to measure the greatest
impact on the environment from the fire retardant waste the sampling was conducted
at more frequent intervals during and following the washing of the fire bombers. Short
term events monitored were the first storm flushing the waste into the ditch and the
first storm causing the discharge of the ditch water into the stream.
The magnitude of the impact of contamination on the environment was then
determined by using criteria established by water quality standards for drinking water
supplies, fisheries, livestock and irrigation water. Also, the magnitude of the fire
retardant contamination was compared to the magnitude of other sources of pollution
in the area to determine the extent of the fire retardant waste problem.
The various possible ways of managing the fire retaidant waste problem were
determined by investigating the various legislative Acts, administrative powers and water
quality standards. In this particular pollution problem there -»c:e various levels of the
government that were potentially involved in its control and regulation. The
governmental agencies that could be involved include: the Waste Management Branch
of the Provincial government, the Department
of Fisheries and Oceans, the
Environmental Protection Service, the Inland Waters Directorate, and the International
Joint
Commission.
The approach taken in this research project is summarized
in Figure 1.1.
4
IMPACT OF FIRE RETARDANT
ON AQUATIC ENVIRONMENT
AT ABBOTSFORD AIRPORT
o
z
oo
=S —
O Ul
at >13
l_>
—I
«*
Z
O
_l
Review and Identify toxicity
problems related to use
of fire retardants and identify
chemical parameters useful
in aquatic monitoring
CO
O
O cc
Determine hydrogeology
and surface & groundwater
flow regime at
Abbotsford Airport
3E
t—
Assessment of amount of
Fire retardant introduced into aquatic environment
and document spatial & temporal distribution
Q.
< u.
h- O
O t—
O X
O UJ
z
DITCH WATER
(3 stations)
<
ce
O
a.
X
UJ
UJ
z
oo
UJ
STREAM WATER
(3 stations)
Monitoring three
Short term events
to determine rate of
transport and distribution
oo
1.
2.
3.
4.
5.
I
GROUNDWATER
(8 piezometers)
Seasonal analysis
August '83 - March '84
13 samples to
determine frequency
and rate of transport
CRITICAL PARAMETERS FOR MONITORING
RATE OF FIRE RETARDANT DISPERSION IN AQUATIC SYSTEM
SPACIAL DISTRIBUTION IN DITCH, STREAM, AND GROUNDWATER
OVERALL IMPACT ON ENVIRONMENT
MANAGEMENT CONSIDERATIONS
Figure 1.1
Research Framework
LABORATORY
SIMULATION
Assessment "
of flow
rate and
soil retention
using column
experiment
Chapter 2
BACKGROUND AND
TITER ATT JRF.
2.1 TNTRODTICTTON TO FTRF, R E T A R D A N T S
Fire retardants
of forest fire retardants
AND
RFVTFW
THFTR
USE
are used extensively in forest fire control. The main advantage
is their ability to inhibit the combustion reaction. The pioneer
of chemical fire retardants
was Gay-Lussac, who in 1820 investigated the fireproofing
action of certain inorganic salts on cellulose (Fraser, 1962). Gay-Lussac; was able to
define two classes of chemical retardants, one which liberated inert gases to dilute
combustible gases and the other that melted to form an oxygen-excluding coating.
In the mid 1950's the chemical retardant
Na Ca borate, was the first retardant
used on a large scale. Fire control agencies found it very desirable as a long term
retardant as it remained effective for weeks, even after drying. But soon after its
introduction Na Ca borate exhibited some objectionable
side-effects. It was found to
have toxic effects on vegetation and to be a soil sterilant which inhibited the entry of
many plant species for more than a year after application (Fenton, 1959; Fahnestock,
1958). Also, the toxic effects were not isolated and spread to surrounding areas due to
rain and groundwater flow. The toxic effects were attributed to the boron component
in the retardant
of which most plants can tolerate only 4 to 5 ppm.
For a short time, bentonite (a clay suspension) was used for fire control but it
had
only short-term properties and in many areas of fire control it was
found to
be inefficient (Phillips and Miller, 1959).
The type of chemical fire retardants
presently
used are the phosphate and
sulphate ammonium salts. The ammonium phosphates were introduced in the early
1960's in some Southern states. They showed impressive retardancy of fire without the
extreme toxic effects that Na Ca borate had (Douglas, 1974). Its ability to retard fire
was found to be directly related .to the amount of phosphate contained in the
5
6
retardant. Other components are added to the salt to inhibit corrosion and to thicken
and
color the mixture (George and Blakely, 1972).
Ammonium sulphate also has become an important fire retardant It is similar
to ammonium phosphate and includes agents to inhibit corrosion and thicken the
solution. Ammonium sulphate is only half as effective as a fire retardant when
compared to ammonium phosphate (Douglas, 1974).
In Canada, the use of chemical fire retardants is concentrated
Canada with British Columbia using approximately
in Western
three times more fire retardants than
the next highest province. The only eastern province to use long term retardants is
New Brunswick (Appendix A). British Columbia used 3,727,000 1 of long term retardant
in the 1983, with a fixe season that was 2 2 % lower than the 10 year average. The
previous year B.C. used 6,785,885 1 of fire retardant, almost double than in the 1983
f l u season (NRC, 1984).
The
types of chemical fire retardants used in Canada are monoammonium
phosphate, diammonium phosphate and ammonium sulphate (Appendix A). The type of
chemical fire retardant used in B.C. is a monoammonium phosphate called PhosChek
XB
manufactured by Monsanto. The chemical and physical description of PhosChek X B
is detailed in Table 2.1. PhosChek X B is manufactured as a powder and when it is
mixed becomes a viscous red slurry.
Fire retardants have the same basic components as agricultural fertilizers along
with a few additives to inhibit corrosion and spoilage, and to thicken and color the
solution. The four main chemical components considered in assessing the impact of the
fixe retardants on the environment axe: nitrogen, phosphorus, corrosion inhibitor, and
the colorant, iron oxide. Fire retardants can reach the water bodies by direct
application, surface runoff and leaching, thereby affecting fish, animals, humans and
vegetation by contamination.
7
T A B L E 2.1 DESCRIPTION OF
GENERAL
DATA
PHOSCHEK
XB
PERCENTAGE
N H H P 0 (11-55-0)
Guar gum thickener
Iron Oxide Coloring
Corrosion Inhibitor
89.0
7.0
2.0
2.0
Mix Density
Viscosity
Salt Content (& by wt in solution)
1.06 kg/1
1500-2000 mPa
10.75
MAP
6.63 P 0
7%
7800
Continuous Flow
Atrial - Fixed Wing
Wet or Dry
Good cohesive properties
High Elasticity
4
2
4
2
Swellage by Volume
Litres of Solution/Tonne Powder
Mixing Procedure
Application Procedure
Storage
Other Remarks
2.2 N I T R O G E N
5
COMPONENT
The nitrogen component in the fire retardanL in the form of ammonium, is
changed by biological, physical and chemical processes which affect its transport to
surficial and groundwaters.
The
various processes are shown schematically in Figure 2.1. There are five
biological transformations of nitrogen. One
biological transformation is immobilization;
this is the assimilation of inorganic nitrogen by microorganisms to form organic
nitrogen forms. Ammonification or mineralization involves the decomposition of organic
nitrogen to ammonium. One
microbial oxidation of NH;
of the most important processes is nitrification by
to NO,
and NO]
the reduction of nitrates or nitrites to N 0
2
. Denitrification, on the other hand is
and N
2
gas. Another biological
transformation is the reduction of nitrogen (N ) to ammonia which is called nitrogen
2
fixation (Keeney, 1983).
There are also various chemical reactions in the soil involving nitrogen.
Ammonia volatilization or sorption is the release and uptake of atmospheric ammonia
by soils or plants. Ammonia exchange is a rapid and reversible process by which
ammonium ions are exchanged
from the soil cation sites to the soil solution. Another
8
Figure 2 . 1
AGRICULTURAL NITROGEN CYCLE
Wastes, Precipitation, Fertilizers
Biological N
Fixation
Organic N, Ammonium N, Nitrate N
INPUTS
nitrification
mineralization 4
Soil
Organic N immobil ization
N,0
„+
u
NO,
SOIL FORMS,
Exch.
NH
4
i Fixed
NH
REACTIONS,
4
ANO
NH.
TRANSPORT
NO,
Oenitrification
Residues
Plant
N20H2
Leaching
RUNOFF
HARVEST
4
RUNOFF
LOSSES 4
ATMOSPHERE
REMOVALS
GROUNDWATER
chemical reaction is the slow entrapment of N H in the clay minerals called ammonia
4
fixation. Chemical denitrification or chemodenitrification is the reaction of nitrites with
soil constituents in acidic conditions or at elevated temperatures to yield N or
2
nitrogen oxides (Keeney, 1983).
The most likely fate of the ammonium ion is nitrification to yield nitrite and
subsequendy nitrate. The chemical sequence is :
NH;
—>
NHjOH ~ >
H N 0
2
2
— > NO",
3
AMMONIA HYDROXYLAMINE PYRUVIC
hrTTRJTE
OXIME
NO} +
NTTTUTE
1/2 0, - - > >
NO",
NITRATE
The optimum p H for nitrification is p H 6 to 8. In acidic water (pH <5) and
by some dissolved inorganic substances, nitrification can be severely reduced (NRC,
91979). Nitrification is also sensitive to a variety of organic compounds with temperature
and oxygen as the limiting factors (Keeney, 1983).
Once the ammonia is oxidized to nitrate it is more mobile in the soil. The
nitrate can be transported to the rhizosphere where it is available for uptake by plants
or through the rhizosphere to the groundwater (NRC, 1979).
The ammonium ion is comparatively immobile in the soil. Its cationic nature
causes it to be adsorbed onto negative adsorption sites on soil, sediment particles and
colloids. The ammonium ion is chemically very similar to potassium and may substitute
for potassium in the soil (NRC, 1979). In soils that have relatively low ion exchange
capacity, frequent and large amounts of water will cause nitrogen to be leached from
the soil more rapidly.
The movement of the nitrates leached into the groundwater are governed by
various aydrologic forces. In groundwater, the rate of th? water flow is a result of
two variables. The first variable called the hydraulic
gradient (dh/dl) is the driving
force which is the change in the water potential per unit distance when the soil is
saturated and the matric and solute forces are zero. Therefore, the driving force is
caused by a gravitational potential energy difference. The other variable is the
hydraulic
conductivity
(K) of the soil which is defined as the ability of the soil to
transmit water (distance/time). Hydraulic conductivity increases with the pore size of the
soil, therefore, sands transmit water much faster than a clay soil. The rate of flow, q,
is a product of the two variables and is calculated using Darcy's Law, q=
K. dh/dl.
There are four main types of contaminant movement in the groundwater. One
type is advection
which depends on the concentration of the contaminant and the
direction and rate of the groundwater flow. Dispersion
is a mixing and spreading
process resulting from local differences in flow velocity and direction. Diffusion
when the contaminant moves down a concentration gradient. Retardation
occurs
occurs when
the contaminant is held back and slowed down by chemical activities such as
precipitation and ion exchange. Nitrate movement in groundwater is governed mainly by
advection and depends on the concentration of nitrate in solution and direction and
rate of groundwater flow (Keeney, 1983).
Nitrate contamination
of groundwater can lead to various adverse effects in
animals and human infants. The health effects are due to the denitrification of nitrates
to nitrites by mtestinal flora found in some animals and in human infants during their
first three to four months of life. The nitrite produced is rapidly absorbed into the
blood from the stomach where it acts as an oxidant converting the Fe(LT) to Fe(III)
in the hemoglobin (Keeney, 1983). The oxidized hemoglobin called methemoglobin is
unabie to transport oxygen causing 'blue babies'; and similarily, possible death to
livestock.
The
route by which fire retardants leads to nitrate poisoning is shown
schematically in Figure 2.2.
Nitrate poisoning by conversion of ammonia to nitrate, absorbed by plants and
eaten by animals is shown as a possible route, in addition to the other routes
described earlier. Some plant species are more likely than others to cause problems.
Oats, for example are considered to be the worst culprits for nitrate poisoning. The
danger of nitrate poisoning of groundwater by fire retardant application is thought to
be very remote and much less dangerous than from range or pasture fertilization
(Dodge, 1970). Nitrate poisoning in livestock is not a widespread problem (NRC, 1978)
but has been attributed to fire retardants a few times (Dodge, 1970). The toxic effect
is similar to humans but the dose of nitrate required in order to be toxic is much
higher and is dependent on the species and its diet
The
Canadian Drinking Water Standard is set at 10 mg/1 N 0 - N . It is felt
3
that this limit ensures reasonable protection to infants of methemoglobinema.
Contamination of stream water is another concern when using fire retardants
because of the large ammonia content in the fire retardant Ammonia causes acute
11
SOIL
AMMONIUM
(Fire
REACTION
L o s t to
Atmosphere
SALT
Retardant)
I
PLANT
REACTION
J
.'
;
1
;
PLANT
Norma
/
L e a c h i ng
\
\ A b normal
Plant
PI a n t
Amino A c i d
11 1 1.1
a
J
;
t e
Norma 1 o r Sma 1 1
Concentration
H i gh
C o n c e n t r a t i or
Ni t r a t e
i
Ni t r a t e
Nitrite
ANIMAL
REACTION
1
Ni t r i t e
Ammon i a
An i ma 1
Amino A c i d
Protei n
Ni t r a t e
Toxi c i ty
Growth and
Good H e a l t h
Figure
2.2
Flow d i a g r a m o f n i t r a t e and
( A d a p t e d f r o m D o d g e , 1970)
Possible
Death
amino
acid
conversion.
toxicity in fish and other stream organisms.
There are natural sources of ammonia in the streams already present due to
sorbed ammonia on particles that axe deposited as sediments in the stream bed. When
there is a change in oxidation conditions, desorption of the ammonia can provide an
input of new ammonia into the watershed. Rainfall is also a source as it can have a
concentration of .03 to .2 mg/1 of ammonia (NRC, 1979).
A study conducted to determine the toxicity of fire retardants on juvenile
salmonids found that fire retardants are toxic to fish. The pH was thought to have an
effect on toxicity of the compounds if the toxicity is due to the ammonia component
of the fire retardant (Dodge, 1970).
12
The main factor in determining the aqueous toxicity of ammonia is the pH of
the water. Only the unionized form of ammonia is toxic whereas the ammonium ion
has little or no toxic effect on fish (NRC, 1979). The ratio of ammonium (NH ) to
4
ammonia (NH ) in an aqueous solution is determined by the following equation in
3
conjunction with Table 2.2:
K = fNH;irOH-1
b
T A B L E 2.2 T E M P E R A T U R E R E L A T E D
K.,
b
VALUES
Tempeia'arre (Celcuis)
0 '
5
10
15
20
25
1.374
1.479
1.570
1.652
1.710
1.774
X
X
X
X
X
X
IO"
1010IO"
IO"
10"
3
5
s
5
5
5
A commercial flow bioassay test was performed in a study with four different
fire retardants on two species of salmonid juveniles. The 24, 48, 96, and 192 hour
Median Tolerance Limits (TLM) ranged from 120 to 940 ppm
for the four fire
retardants used in the experiment For the PhosChek retardants the T L M
ranged from
120 to 191 ppm. The Median Tolerance Limit is the concentration of the tested
retardant at which 50% of the test animals are able to survive for a specified time
(Blahm et al., 1972).
The retardants used in the study along with their percentage of potential
ammonia is shown in Table 2.3. PhosChek X B has a potential 1 3 % of ammonia which
is the lowest of the Fixe retardants currently being used (Monsanto, 1978). In Table
2.3 it is apparent that different mix ratios axe used in the field. Thexefore, even
though the fish tested had greater tolerance to Fixe-Trol in this experiment it may be
13
a different ratio used in the field.
T A B L E 2.3 POTENTIAL A M M O N I A IN VARIOUS FIRE
Retardant
Fire-Trol
Fire-Trol
PhosChek
PhosChek
RETARDANTS
Potential Ammonia (%)
931
100
202
259
12.0
16.0
22.4
24.5
Blahm and coworkers (1972) found that the fish have a distinct behavioral
change when 100% mortality did not occur. Most of the fish displayed a loss of
equilibrium within a few hours. When 100% mortality occurred at the higher
concentrations a loss of equilibrium was not evident when they were alive, but the
dead fish had swollen bodies. Therefore, it was thought that this might indicate the
retardants had an effect on the .fish's osmoregulatory
mechanism.
During firefighting operations there is a good chance that the fire retardants
will enter streams due to aerial application of the retardants. The chemical and
physical nature of the stream is important in assessing the impact the fire retardants
will have on the stream
The chemical nature of streams is highly variable due to
varying patterns in runoff, precipitation and other factors. The turbulent flow of the
stream water results in the mixing and uniform distribution of the dissolved substances
throughout
the water (NRC, 1979). The diluting effect of the stream depends on its
ability to mix laterally (across the stream), vertically as well as longitudinally
(elongation in downstream direction) (van Meter and Hardy, 1975). Generally, the
greater the mean velocity of the stream the less there is longitudinal mixing. A
lower
velocity will permit turbulent eddies to have a greater effect on the mixing process. '
There is a threat of severe fish mortality in small streams with low velocities
when fire retardants enter in a single dose. Van
problem and
Meter and
developed a method to determine how
Hardy (1975) studied this
long it would take for a single
dose of fire retardant to dilute to levels that could be tolerated by fish. In smaller
streams the concentration remains higher for longer distances and
times, therefore, the
peak is more spread out and the exposure time longer. They assume. that if the fish
made it through the peak concentation then it will most likely survive the whole
event
The
toxicity of ammonia to fish at 50%
Figure 2.3. The
and
10% mortality levels is shown in
outer edge of the curve indicates a worst case scenario and was
in predicting the effect of fire retardants in streams (Van
A
study conducted by Brown and
ammonia concentrations between 0.5 and
Meter and
used
Hardy, 1975).
coworkers (1969) looked at fish exposed to
1.5 tiroes the 48 hr L C
5 0
concentration. They
found the fish responded as if they were exposed to the mean concentration when
they alternated the fish at one
water. The
from one
within two
and
two hour intervals between fresh and
toxicity of ammonia to fish was
to two
contaminated
greater when the periodicity was
increased
hours. They felt this indicated an irreversible change in the fish
hours that did not occur within one
hour. Therefore, fish could be
irreversibly effected depending on the ability of the stream to dilute the dose of fire
retardant which is deposited in i t
2.3 P H O S P H O R U S C O M P O N E N T
The
other major component of PhosChek XB
is ortho-phosphates. Phosphorus
is an essential nutrient of all forms of life for growth. Phosphorus (P) is in available
forms in the soil and
from 0.03
mg/1
to 3.9 mg/1.
water for plants and animals. P concentration in soils range
The
concentration of P in soil solutions are seldom above 0.3
in agricultural soils, and 0.01
mg/1
in subsoils. ("Walsh et al, 1976)
A
high
15
100
B
<u
u
c
»o
u
*
o
.1
0.1
I—
.0
concentration of P in soil is desirable in agricultural land where it helps increase its
biological productivity. But, in water, a high concentration is very undesirable for it
promotes eutrophication.
A
simplistic diagram of P interactions when a waste containing P is applied to
soil is shown in Figure 2.4. The
inorganic phosphate is applied to soil where the P
forms include: P bound in organic matter such as humus, P as phosphate anions in
the soil solution, and P bound in inorganic P forms. In Arrow 1 the added and
native organic P forms are slowly mineralized by soil microorganisms through the
decomposition process. Some of this mineralized P can be readsorbed (Arrow 2) and
thus is temporarily immobilized
by microbes. Dissolved P is the form that plants take
from the soil solution for growth and
development and
is only a small fraction of
total P in the soil (Arrow 3). Leaching occurs from this form of P. The
dissolved P
is in equilibrium with a large amount of P that is bound in the inorganic form
Figure 2.5 Phosphorus Interactions in Soils
Wastes, F e r t i l i z e r s , Animal Waste, Plant Debris
INPUTS
Organic P, Inorganic P
SOIL FORMS
AND
Phosphorus Bound
Dissolved
Phosphorus Bound
Organic Forms
Phosphorus
Inorganic Forms
(ie
inositols)
H P0
2
4
REACTIONS
Rock
Phosphate
(apatite)
Ca^ /POj
OUTPUTS
Surface
Runoff
and
Erosion
Harvest
Adsorbed
Phosphate
Precipi tated
Phosphate
Al^/PoJ"
Ca /P0 "
2+
Leaching
(Adapted from Loehr, et a l . , 1979)
3
17
(Arrow 4) as alurmnum, iron and calcium
phosphates (Loehr et al., 1979)
Phosphate ions are mainly retained in the soil through adsorption and
precipitation reactions with immobilization-rmneralization
reactions also occurring. The
particular type of reaction and type of endproduct is dependent on the composition of
thd soil media, p H of the solution and the residence
time of P in the soil.
Phosphorus precipitation in soils involve calcium, iron, and aluminum ions.
Precipitation reactions are a function of p H with calcium phosphates predominating at
above p H 6 to 7 and iron and aluminum phosphates predominately at below p H 6 to
7. Figure 2.5 shows the general relationships between soil p H and phosphorus
reactions.
Precipitation-dissolution reaction rates in soils are usually slow compared to
sorption reaction rates. Most of the ortho-phosphates are removed from soil solutions
by sorption mechanisms.
Adsorption
onto hydrous oxides of iron and aluminum is a major component in
phosphate removal. The mechanism involves the retention of P by iron hydrous oxide
surfaces by a ligand exchange between -OHj or = O H
illustrated in the equations
below: (Ryden et aL, 1977a)
Gel
/
Fe-OH;
Fe-H,P0
+ H,PO;
\
-
Fe-OH
/
+ H,PO;
\
-
\
Fe-OH
/
Fe-OH
Gel
/
\
3
Fe-OH
Fe — O H
/
H 0
+
\
Fe — O H
Gei
4
/
\
Condensation
Fe-HjPO.
+ OHFe-H,PO«
Fe-O
O
\ //
Fe-O
/
P
\
+ H 0
2
OH
IS
Percentage
Distribution
Figure
2.6
Soil
pH and
pH o f
(Adaoted from Loehr, et a l . ,
The
Phosphorus
Soil
Reactions
Solution
1979)
P immobilization potential is dependent on the soil and its potential P
sorping surfaces. Finer textured soils have a greater capacity to immobilize P than
coarser textured soils mainly due to their greater total surface area. Iron, aluminum
and calcium bearing minerals have a greater ability to sorb P due to the reactions of
P with these elements (Douglas, 1974;
Stewart, 1964). The sorption capacities shown in
Table 2.4 for various soils are determined from sorption isotherms, at equilibrium, with
2 x 10-" M
P (Sawhney and Hill, 1975). For example, Ellis (1973) found that
minimum adsorption in dune sand and maximum adsorption in Warsaw loam. The high
capacity in Warsaw loam was accounted for by very high aluminum concentrations.
19
T A B L E 2.4 P SORPTION CAPACITIES OF
Soil
Parent Material
Merrimac, si
Stockbridge, 1
Buston, sil
Charlton, fsl
Sandy, gravelly terraces
Firm limestone till
I^aistrine silts & clays
Loose till of granite &
gneiss
Losse till of Trissic
sandstone & shale
Compact till of gneiss &
schist
Cheshire, fsl
Paxton, fsl
The
SOILS
Sorption Capacity (mg/lOOg)
9.0
14.5
20.0
21.8
27.5
29.0
availability of P in the soil is highly dependent on time. One
way
to
illustrate this relationship is by the equilibrium reaction:
P sorbed < = = = >
P in solution < = = = >
P precipitated
If soluble P is added or removed the immediate reaction will be by P being adsorped
but at equilibrium the precipitate forms will control the P in solution. This system
will ctyjstantly be in disequilibrium and
to the right under conditions of
discontinuous
addition of wastewaters.
Generally, little P is lost from soils by leaching because of the strong affinity
of phosphate for soil components. However, some phosphates in the soil solution can
leach because of the equilibrium between the P in solution and
that in the solid
phases.
2.4 C O R R O S I O N INHIBITOR
The
corrosion inhibitor component is the most toxic component in the fire
retardant for animals and
people. (Monsanto, 1978)
Even though they are very toxic,
corrosion inhibitors constitute a relatively low hazard as shown in Table 2.5. The
of corrosion inhibitor contained
Monsanto had
in PhosChek XB
type
is unknown as it is a trade secret
previously been using sodium dichromate. as a corrosion inhibitor, but it
is not contained
in PhosChek
XB.
Table 2.5
TOXICITY OF CORROSION INHIBITORS
An i ma 1
tested
Method
Sodium mercaptobenzothiozole
rats
oral
Sodium dichromate
rats
guinea
pig
intramuc.
subcut.
Sodium fluorosi1icate
rats
guinea
pig
Thiourea
Inhibi tor
Dosage per unit
of body weight -
Amount of
inhibitor per
mixed l i t e r '
kg/1
Quantity Injested
to be toxic or
lethal to 90kg man
Mixed l i t e r
mg/kg
k<i/90kg
man
Degree
3968
.36
LD 50
2. 2 x 10"
( .IX of premix)
1681
140
51
.0127
.0046
TO Lo
TO Lo
4. 4 x 10"
( 2.0% of premix)
3.0
oral
oral
125
250
.011
.023
LO 50
TO Lo
2. 2 x 10"
( 1.OX of premix)
4.9
10.6
women
oral
1660
.011
TD Lo
2..2 x 10"
( 1.0% of premix)
4.9
Ammonium fluoride
guinea
pig
oral
150
.011
LD Lo
2 .2 x 10"
( 1.0% of premix)
4.9
Sodium n i t r i t e
rats
oral
85
.011
LD 50
2..2 x 10"
( 1.0% of premix)
4.9
Oimethylamine
rats
oral
698
.011
LD 50
2 .2 x 10"
( 1.0% of premix)
4.9
Amnion ium
t iocyanate
mouse
interperi toneal
500
.011
LD Lo
2 .2 x 10~
( 1.0% of premix)
4.9
4
3
3
3
3
3
3
3
1.1
Aniline sulfate
2 .2 x 10"
( 1.0% of premix)
No data
Sodium ferrocyanide
3 .2 x IO"
( 1.5% of premix)
No data
LD 50 - l e t h a l dosage to 50 percent o f
ID Lo - lowest published l e t h a l dose
TO Lu - lowest published t o x i c dose
3
3
subjects
For lack of exact amounts and v a r i a b i l i t y between
p r o d u c t s , assume:
a) dry dowder or c o n c e n t r a t e is 20% of mixed l i t e r
b) mixed l i t e r weiyhs I kg
c) 1 o l premixed bay or c o n c e n t r a t e is rough estimate
The
assumption underlying the toxicity studies on corrosion inhibitiors was that
mice, rats and man have the same degree of toxicity. For example, one must ingest
one
pound of powdered retardant or one quart of undiluted liquid concentrate in order
for the results to be fatal. The greatest danger would occur at the mixing station, but
only i f an unusual incident happens. In the field, only skin contact is likely to occur
with a veTy slim chance that a portion of the fire retardant would be ingested.
Animals, may eat some of the retardant due to the salty taste, but it would probably
be very unappetizing after one taste. Intensive bioassay tests were performed with
PhosChek X B and it was found to be nontoxic to animals down to the size of a
rabbit under normal contact with a concentrated
solution (Monsanto, 1978).
There were no studies done on the effects of the corrosion inhibitor component
in water. Since the type of corrosion inhibitor used in PhosChek X B is unknown, it
is difficult to determine the impact it may aave on the aquatic environment and its
possible transformations in the soil and groundwater.
2.5 COT .OR A NT
The
colorant used, iron oxide, is a naturally occurring inert substance which
creates no environmental
hazards. The only complaint in the use of the iron oxide is
because of the visual aspect of the red color in certain instances (Monsanto, 1978).
Chapter 3
MFJHQPS
3.1 SAMPT.TNO DFSTON
A sampling design was established to fulfill the objectives of the study. The sampling
design incorporated both field work and a laboratory study. The study involving
field
work had three parts. A long term sampling field study was set up with nine field
locations (three ditch stations, three stream stations, and three groundwater
and thirteen sampling dates. It was designed to establish background
locations)
conditions and to
determine when and where contamination occurred in the various environments.
Two
short term events were also monitored. The first involved the first storm event
whereby the fire retardant waste was washed into the. ditch from the drainage system.
The impact on the ditch water was monitored at two to four hour intervals using an
automatic sampling unit while the stream and groundwater
were monitored for four
days. The second event monitored the water quality of the discharge from the ditch
into the stream. The discharge from the ditch was monitored at two to four hour
intervals using an automatic sampling unit over a period of three days while the
stream was monitored before and after the event A laboratory experiment was
designed to simulate the groundwater
contamination in order to determine the rate of
movement through the soil, and the chemical transformations of the solution in the
soil column. In Figure 3.1 the sampling design is shown using a flowchart
3.1.1 S A M P L I N G
DESIGN
- FTF.T.D W O R K
3.1.1.1 Field Locations
To determine the impact of the ditch water on the groundwater, the
piezometer nests were installed downgradient
from the ditch at different distances
and directions. The three locations of the piezometer nests are shown in Figure
22
FIGURE 3.1 FLOWCHART OF SAMPLING DESIGN
PROBLEM
SHORT
TERM
1 X 72 Hrs
IX 9 Hrs
DITCH
SHORT
TERM
1 X 24 Hrs
SHORT TERM
LAB STUOY
LONG
TERM
Aug. - Mi»r.
13 Sets
STREAM
SIMULATE
GROUNDWATER
CONTAMINATION
GROUND
WATER
TIME
RATE
PARAMETER
RESIDUE
TIME
AMOUNT
PARAMETER
Effects On
Ditch,
Stream,
Groundwater
Parameters
Best For
Monitoring
Flow Regime
Hydrogeology
2 Cones.
45 Hours
Relationships
Between
Components
Comparts ion of
Lab Simulation
and Field
Observations
3.1.2. At location PI, two piezometers were installed at various depths. At
locations P2 and P3, three piezometers were installed at various depths. By
installing the piezometers at various depths, the vertical location of the plume
can be determined. The
drilling program is described in Section 3.14.
To detenriine the impact of the ditch water on the stream water three
sampling locations were chosen. In Figure 3.3, the three locations are shown, SI,
above the point where the ditch drains into the stream, and S2, below the point
where the ditch (tains into the stream, and S3, the point where the stream
crosses the international boundxy into the United States.
The
ditch water was sampled at three locations, they are shown in
Figure 3.2. The
ditch water was sampled at the outfall, D1A,
in the middle of
the ditch, DIB, and at the other end of the standing ditch water,
D1C.
The locations of the sediment sampling are the same as for the water
sampling, but with two samples taken at each location.
To measure the water quality of the water entering the ditch, the
automatic sampling unit was located directly under the drainage outfall in the
ditch.
To measure the impact of the ditch water entering the stream the
automatic sampling unit • was located close to the point where the ditch enters
the stream in the ditch. The location, DID,
is shown in Figure 3.2.
3.1.1.2 Frequency
A
long term monitoring program was designed to determine the
background chemistry, flow regime and the effects of the fire retardant on the
ditch, stream and ground water.
A
complete sampling set included eight groundwater samples, three stream
water samples and three ditch water samples. There were thirteen sets taken
between August, 1983 to March, 1984. The
time interval varied from one day to
27
three months, with a shorter interval when a greater impact was expected. A
greater impact on the environment was expected at the first heavy rainfall after
plane washing had taken place.
To determine the effect of the fire retardant being washed into the ditch
by a storm event an automatic sampling unit was set up to take continous water
samples of the ditch at various time intervals over five days, October 19 to
October 23, 1983.
To determine- the impact of the ditch water on the stream, an automatic
sampling unit. wa$ set up to take samples at various time intervals over three
days, November 14 to November 16, 1983.
Sediment samples from the ditch were taken after the fire retardant was
deposited in the ditch on November 2, 1983. Another set of samples were taken
on March 6, 1934 in order to determine i f there was a significant cnange in
the sediment concentration over this time period.
3.1.1.3 Parameters
Measured
The parameters measured in the water were: pH, specific conductance,
nitrate-nitrogen, ammonium-nitrogen, ortho-phosphorus, total phosphorus, iron,
calcium, magnesium sodium, potassium, and chromium.
The parameters measured in the sediment were: total phosphorus, iron,
calcium, magnesium, sodium, potassium, and chromium
3.1.2 P R IT ,1 .TNG
P R O G R A M TO
TNSTAI.T. PTP7.QMFTFR S
Drilling commenced July 19, 1983 in unconfined sands and gravels located
near the southwest comer of Abbotsford Airport (Figure 3.3). Three bore holes
were constructed and piezometers installed to determine groundwater flow direction
and groundwater flow rate. The
two methods available were Air Rotary and
Cable Tool. Air Rotary is the fastest drilling method although it does not
provide good stratigraphy. The Cable Tool method is three to four times slower
but provides very good stratigraphy.
The type of drilling chosen for the project was an A i r Rotary truck
mounted drill rig. It enabled three holes to be drilled in one day. Water was
not used during the drilling process which ensured that groundwater chemistry
would not be significantly altered.
The locations of the three holes (Figure 3.2) were chosen in order to
monitor the groundwater for contamination resulting from ditch water recharge.
Borehole locations were sited in a rough equilateral triangle to facilitate
calculations of groundwater flow directions. The depth to the water table was
approximately 2.5 to 3.0 m. The boreholes were drilled to a depth of
approximately 6.1 m. Samples of the geological units were taken at different
depl&s during the drilling to be u ^ d for sieve analysis calulations of the
hydraulic conductivity.
Piezometer nests were installed in each hole. (See Figure 3.4) The nests
had two (PI) and three (P2, P3) piezometers with screens installed at various
depth intervals. The vertical location of the contaminant plume could be
determined
using this method.
The piezometer casing material was 2.54 cm ID PVC
tubing. The slots
for the screening were cut with a hacksaw and the screening length varied from
53 cm to 69 cm
The bottom of the piezometers were capped and no glue was
used as the piezometer's length was only 6.1 m.
After the piezometer nests were installed the holes were backfilled with
drill cuttings. Bentonite was used at the top of the casing to seal the holes and
to prevent vertical migration of ponded surface water.
metres
above
sea level
Figure 3.4
~ >er*
PIEZOMETER
ground
level
Sl\
52
NEST
ground
level
CONSTRUCTION
SO
51
50
ground
level
49
49
48
48
47
•47
46
•46
45
44
P3
•45
PI
P2
4-f
ID
30
3.1.3 L A B O R A T O R Y FXPFRTMF.NT
A
laboratory experiment was designed to simulate the groundwater-
contamination by PhosChek XB. It involved the application of a solution of
PhosChek XB
onto a soil column to determine the rate of leaching and also the
chemical transformations of the solution in the soil column.
3.1.3.1 Materials
The soil used was obtained in June, 1983 from the dry section of the
ditch at the Abbotsford Airport The soil was then airdryed and seived to less
than 2 mm.
The fire retardant, Phoschek XB, was applied on the coiumns using
70 mis of 2000 and 1000 ppm
cm
and 5.0 cm
solutions. The
diameter of the columns was
5.8
with a length of approximately 35 - 40 cm. A l l the equipment
used was acid washed with 6N
HCI. Polyethylene cubes were used at the
bottom to the columns for 3 cm. The set up is shown in Figure 3.5.
3.1.3.2 Procedure
The soil was packed in the columns to a depth of 30 cm. The
columns
were then saturated with distilled water and left for 48 hours to equilibrate.
After 48 hours the flow rate was set at approximately 1.5 ml/mir with the
constant head apparatus. The coiumns were rinsed for 2 hours before the fire
i
retardant solution was added. After 70 ml of the fire retardant solution
was
added, three more applications of water were rinsed through the columns before
the
constant head apparatus was utilized. Three columns were used, one for the
control and two experimental columns.
3.1.3.3 Sampling Design
The effluent from the columns was monitored every half hour by
measuring the specific conductance. Also, water samples were taken at different
time intervals to substantiate more fully the rate of movement of the fire
31
50 ml
Graduated
Cy1 i n d e r
Figure
3.5
COLUMN SET UP
32
retardant in the soil columns.
The fire retardant solution used was analyzed to determine the input of
the
various components on the soil columns.
The
effluent was measured to determine the output of various components
over time and the total output of the components from each soil column.
After the initial experiment, the soil in the columns was separated at 15
cm depth intervals yielding, top, middle, and bottom soils. Each layer from each
column was analyzed for various components of the fire retardent.
The parameters measured in the . water and soil samples are the same as
in the field study with the exception of ortho-phosphate in the water samples.
3.2 S A MPT.ING PROCETOIJRES
All bottles used were prepared and preserved according to guidelines set by
Environment Canada (1983).
After the piezometers were installed the water in the piezometers was pumped
out for twenty minutes to clean out the system The procedure used throughout the
sampling period included pumping the groundwater for ten minutes or until clear, then
taking a water sample and measuring the temperature and pH, rinsing sample bottles
three times with water being sampled, then taking the water sample. Separate samples
were taken for metals, nitrogen, and phosphorus determinations. The sample taken for
metals analysis was filtered and then acidify with H N 0
3
to less than pH 2.
The samples were then transported to the laboratory in an ice chest for
chemical analysis and analyzed within 48 hours.
Grab samples were collected from the middle of the stream and ditch, and
were treated the same way as the groundwater samples.
The sample bottles from the ISCO automatic water sampler were picked up, •
put in the ice chest and immediately brought into the laboratory for analysis. Aliquots
were taken from the sample bottles for metal analysis. The aliquots were filtered and
acidified.
Sediment samples from the ditch were taken by scraping the bottom of the
ditch with the sample bottle until a representative sample was taken. The bottles were
then put in the ice chest and brought to the laboratory.
3.3
CHFMTCAT.
ANALYSTS
3.3.1 WATER
SAMPLES
A Western Scientific p H D pH meter standardized with buffers of pH 4
and 7 was used to measure the pH in the field.
Dissolved oxygen was determined at the field using a Hach kit specific
for dissolved oxygen.
The specific conductance of the water samples was measured
Radiometer-Copenhagen
using a
conductivity meter.
A Perkin Elmer 306 Atomic Absorption Spectrophotometer was used to
determine Ca, Mg, Na, IC, and Fe in the water samples. The standards used
were in the same acid matrix as the water samples. The water samples were
either read directly or diluted to be within the range of the Standard solutions.
(Environment Canada, 1979a)
The Varian Graphite Furnace was used to determine the concentration of
chromium in the water samples. The samples were either diluted or measured
directly depending on standards used.
A spectrophotometric method using chromotropic acid was used to
determine nitrate-nitrogen in the water samples. (West and Ramachandran, 1966)
A colorimetric procedure using an E D T A solution, phenol solution, and
hypochlorite solution was used to determine the amount of ammonium-nitrogen
34
in the water samples. (Beecher and Witten, 1970)
Ortho-phosphate in the samples was determined colormetrically using the
Stannous Chloride method. (Environment Canada, 1979a)
For
total phosphorus determinations the water samples were autoclaved in
order that all the phosphorus would be in the ortho-phosphate form. The
samples were then analyzed colormetrically by the Ascorbic Acid method, using a
Technicon Autoanalyzer II. (Environment Canada, 1979)
3.3.2 SQJJ
AND
SFDTNfFNT SAMPT.FS
Total phosphorus was determined by digesting the soil with Fleischmann's
acid, the or do-phosphate produced was then determined colormetrically using the
Ascorbic Acid method. (Environment Canada, 1979a)
Total raerals in the soil was determined by digesting the soil in a Teflon
bomb using a mixture of hydrofluoric, nitric and perchloric acids. The
concentration of the various metals were then determined on the Perkin-Elmer
306 Atomic Absorption Spectophotometer. Chromium was measured on the Varian
Graphite Furnace. (Environment Canada, 1979)
3.4 HYDRAITTJC CONDI KTTTvTTY
The hydraulic conductivity was estimated by grain size analysis on the samples taken
during the drilling expedition. The samples were wet seived using 2 mm,
mm,
.25 mm,
Two
and .106 mm
1 mm,
.5
seives, air dryed and then weighed.
different equations were used to estimate the hydraulic conductivity. The
first was Hazens formula which uses d
10
as the effective grain size. The second
method used was developed by Masch and Denny ( 1966). This method uses grain
size gradation curves, the median grain size, d
50
and the inclusive standard deviation.
35
3.5 STATISTICAL ANALYSTS
3.5.1 O V r a V T F W
Since most physical parameters are by nature heterogenic, nonparametric
statistics were used to examine most of the data collected. The techniques used
were as follows:
1.
Mann-Whitney U Test
2.
Trend
3.
Correlation
4.
Multivariante Cluster
A
Analysis
Analysis
flowchart showing the statistical design is shown in Figure 3.6. The three
environments are defined as ditch water, stream water, and groundwater. There
are three ditch water locatioai. D1A, DIB, D1C. The three stream water
locations are SI, S2, and S3. The three groundwater locations are PI, P2, and
P3.
3.5.2 M A N N - W H T T N F Y II TF.ST
The
Mann Whitney U Test was used to determine if there was
significant differences between environments over time of each parameter, and
between groundwater locations over time of each parameter.
It was also used for significant differences between
1.
PI, P2, P3 over time between parameters
2.
Groundwater, Stream water, Ditch water over time between parameter
3.
SI, S2, S3 over time between parameters
4.
Column soil samples beween parameters.
»
F i g u r e 3.6
SPACIAL
ANALYSIS
Non p a r a m e t r i c
S i g n i f i c a n c e Test
DW vs GW vs SW
D i f f e r e n c e s Between
DW, GW, SW
f o r each
Sampling Date
Statistical
TEMPORAL
ANALYSIS
RELATIONSHIPS
Non p a r a m e t r i c
S i g n i f i c a n c e Test
Comparing events
Craphs
Differences Within
and Between GW,
SW, and DW
Over Time
Design
C o r r e l a t ion
Cluster
Relatlonships
DW,
SW,
GW
Analysis
Relationships
DW, SW, GW
and
TIME
Relatlonships
Between
D i t c h Sediment &
Water
3.5.3 TREND ANALYSIS
Trend analysis was used for the analysis of each environment in the
comparison of the trends of the other environments and for the analysis of
groundwater trends between locations and depths. It allowed for background
relationships to be established and events to be identified within each
environment It also enabled the data to be analyzed spatially and temporally.
The graphs produced were single parameter values over time of up to three
locations on each graph.
3.5.4 COR RET ATTON
. Standard correlation analysis was used with each environment correlated
against all other environments for each parameter on each sampling date. The
analysis involved th?. average value of the parameter on the sampling date of
each environment being correlated. The three locations for the groundwater were
also correlated in the same manner.
3.5.5 MUTXTVARIATF CLUSTER
ANALYSTS
Hierarchical grouping analysis was performed on the data set using the
computer program U B C CGROUP. The data set utilized was from the August
31, 1983 to January 12, 1984 sampling dates. Each sample location was used at
each date as an independant data set The similarity in water chemistry between
the different samples was then determined by cluster analysis based on twelve
chemical parameters. The resulting cluster groups provided a mechanism to
classify all water samples into distinct chemical groups on the basis of
multi-parameter data. Two sets of data were abstracted from the analysis, an all
data set and a groundwater data set
38
3.6 WATER DATA
Precipitation
Hourly precipitation records were obtained from Environment Canada for
Abbotsford airport
Well Records
Well records were obtained from the National Hydrology Research Division of
Environment Canada in Vancouver.
Chapter 4
DESCRIPTION O F THF, S T U D Y ARF.A
4.1 G F N F R A I . DFSCRTPTTON
The
study area was located in the extreme southwest of mainland
British
Columbia in the Lower Fraser Valley. It is bounded by the Canada-United States of
America
border to the south and the cities of Clearbrook and Abbotsford to the
north. (Figure 4.1)
Abbotsford Airport is situated in a rural area in the municipality of Matsqui.
The
Airport serves as an alternative international airport for the Vancouver International
Airport during emergencies and bad weather. It is a base foi several companies,
organizations and flight schools. It is also the host for an annual airshow during
August
4.2 SIJRFTCTAL GF.OI.OGY
The
Abbotsford outwash plain was developed
from the downwashing of an ice mass
which had occupied the Sumas Valley to the east The outwash plain covers an area
of about 51.8 km extending south and west of Abbotsford to and across the United
States border. The outwash sand and gravel materials are not uniformily distributed.
They vary between 0 and 30 m
in depth and are underlain with blue clay (Halstead,
1977).
The
surficial geology of the area is shown in Figure 4.2. The study area lies
near the western boundary of the outwash plain in the southwest region of the
Airport property and Fishtrap Creek. The surficial geology of the Abbotsford Airport is
part of the Sumas Drift which contains recessional glariofluvial
deposits of sand and
gravel up to 40 m thick (Armstrong, 1980), with the normal thickness between 5 to
25 m. The recessional channel and floodplain deposits were laid down by postglacial
39
-p.
o
F i g u r e 4.2
Surficial
Geology o f Study Area
(Adapted from A r m s t r o n g , 1980)-
LEGEND
QUATERNARY
POSTGLACIAL
S A U S H SEDIMENTS
;oooooooo
3 O O 0 Q O 0 O 0
9 O O O 0 O O O O
I O O O O O O O O
looooeoooi
SAb-9
TI
SAh-k
Bog,
swamp,
silty
clay
and
loam
or Salish
shallow
lacustrine
sediments
overbank
deposits);
overlying
Fraser
Stream
deposits,
lowland
stream
includes
deposited
with
sand
Fraser
into
River
maximum
and
clayey
Eolian
silt at the outer
edges
SAt
deposits
than
places
gravel
gravel
in part
intermixed
(SAq,
deposits
gravel
and
SAh,
in
from
area:
gravel,
thick
thick
loam;
grades
channel
till sand
15 to 45 cm
sediments:
clay
lacustrine
stream
channel
loam
and
minor
minor
r),
sand,
up
silt,
thick
windblown
have
1 m thick.
Salish
organic
S A i , lloodplain
Valley;
ol a Ian-shaped
with
15 m; S A j , mountain
stream
and
and
River
up to 8+m
overbank
loam,
in Sumas
Fg,h) and
S A k , lowland
and
that the
(Fraser
to clay
up to 8 m thick;
River
Sedimentsi
deposits:
material;
sand
peat
/ill, lloodplain,
silt loam,
( F c . d , . g . h)
to S A b except
loam
sandy
organic
Sediments
silt, and
sandy
overbank
organic
silt, up to 5 m
Eolian
SAt
channel
till and
by Chilliwack
thickness
to 10 m thick;
organic
peat,
River
(Fd); S A e , upland
Sediments
channel
disseminated
Fraser
( S A q , r); S A c , similar
S A d , lowland
contains
through
overlying
by up to 1 m ol silt loam,
River
and
S A b . low.and
deposits:
thlcx
deposits
are overlain
sand
lake
0.3 to 10+m
sand,
been
mapped
In addition
122'25'W
are mantled
Included
are areas
silt, and
most
as a separate
pre-Salish
by windblown
1 to 8 m
unit
and
thick
where
Sediments
sand
as T and
mapped
silt loam,
they
exposed
silt 5 cm
P T up to at least
to 1 m
1000
are
more
east
ol
thick.
m
elevation
PLEISTOCENE
S U M A S DRIFT
Recessional
deposits
normal
Sa.a.l
glaciolluvial
laid
range
thick,
Sd
S i , similar
and
and
clasts
of Fort
lorm
Langley
ol Fort
ol
Langley
and
gravel
glaciomarine
sand
and
sand
up
sand
containing
( F L c ) , 2 to 5 m
containing
till
containing
lenses
thick,
till lenses
( F L c ) , 5 to 2S m thick,
sediments
thick,
sand
( F L c ) , 2 to 5 m
sediments
gravel
glaciomarine
and
sediments
and
and
outwash
gravel
glaciomarine
lloodplain
up to 40 m
gravel
that it is pitted
Langley
and
sand
deltaic
S b , ice-contact
deposits:
F L b . t : S d , ice-contact
overlying
clasts
to S a except
ol Fort
channel
gravel
m; Se, proglacial
F L c ; S c . ice-contact
overlying
clasts
streams;
5-25
ice-contact
till lenses
S a . recessional
deposits:
by proglacial
ol thickness
to 10 m thick;
Recessional
Sb.c
down
and
in
the
kames
FORT L A N G L E Y FORMATION
Glaciomarine
How
FLa.c.d
deposits,
till with
sandy
marine
loam
F L c and
F L d ; F L c . glaciomarine
silty
to sandy
clay
F L c and
Lodgment
thick;
overlying
shown
and
S g , sandy
Fort
loam
flow
till and
Langley
may
stony
unit
only
glaciomarine
generally
where
ol and
clay,
in mappable
substratilied
drilt,
In most
and
with
intermixed
0.5 to 2 m thick.
sediments
till
interbedded
8 to 100 m thick;
intimately
it occurs
till and
drilt
tilt; F L a . lodgment
minor
clasts
silt to loamy
till: Sf. sandy
substratilied
and
contain
up to 30 m thick,
as a separate
minor
sediments,
matrix;
FLd.
with
exposures
2 to 10 m
places
(FLc)
SI.9
(Adapted from Armstrong, 1980)
43
streams (Armstrong, 1980). The Abbotsford outwash is shown in geological cross-sections
in Figures 4.3, 4.4, 4.5, and 4.6.
The soil material of this area is 20-50 cm of medium textured eolian deposits
overlying the gravelly glacial outwash. The soil classification for this area is Ortho
Humic Ferric Podzol (Luttmerding, 1980).
The area directly west of the Airport around Fishtrap Creek contains postglacial
poorly drained bog Salish sediments. This consists of swamp and shallow lake deposits
and could contain upland peat up to 8 m thick (Armstrong, 1980). The soil material
k
this area contains 40-160 cm of well decomposed organic material underlain by fine
textured glaciomarine deposits. The drainage is very poor and has a perched water
table. The soil classification is Ferric Humisol (Luttmerding, 1980).
North and south of the Airport along Fishtrap Creek the surficial geology
changes to stream deposits which include primarily channel fill floodplain and overbank
sediments. Also, lowland steam channel Till overbank sandy loam and clay loam may
be present along with disseminated organic materials (Armstrong, 1980). The soil
material is medium to moderately
fine textured local stream deposits. This area also
has very poor drainage and is subject to flooding. The soil classification is Rego
Gleysol (Luttmerding, 1980).
4.3 GROTJNDWATFR
4.3.1
fTYT)ROT,OGY
O R O I T N T Y W A T F R
F L O W
The area encompassing the Abbotsford Airport overlies an unconfined
aquifer called the Abbotsford Upland Aquifer. The total area of the aquifer is
estimated to be 52 square kilometers. Hydrogeological studies of the Abbotsford
Upland Aquifer have indicated a major groundwater divide in the region of the
Abbotsford Airport (Halstead, 1977). It is therefore likely that the groundwater
Figure 4.3
Location of Geological Cross Sections
GEOLOGICAL CROSS SECTION
METRES
ABOVE
SEA LEVEL
Northwest
Southeast
ID
200f
100
•km
fo % it"
VERTICAL
EXAGGERATION lOOi
Figure 4.4 Geological Cross Section
A-A
1
GEOLOGICAL
igure 4.5 Geological Cross Section
B-B'
CROSS
SECTION
GEOLOGICAL
CROSS
SECTION
C - C
N o r ,
Figure 4.6
h
Geological Cross Section C-C
South
48
moves both west and east from the Airport and discharges through Fishtrap
Creek to the west and through the springs along the eastern flank of the
Upland near the fish hatchery. (Figure 4.7)
Well records were used to determine the regional groundwater flow
directions that confirmed
that the Abbotsford
Airport overlies a groundwater
drainage divide. On the eastern side of the drainage divide, the groundwater
flows southeasterly towards the upland
flank discharging at the springs. (Appendix
B) On the western side of the groundwater drainage divide the groundwater
flow? southwest to Fishtrap Creek. This was confirmed
by the hydraulic head
readings from the piezometers installed at the Airport (Table 4.2) In the winter
month* the flow direction was predominately
westerly towards Fishtrap Creek.
(See Figure 4.8)
Groundwater flow rates in the study area were calculated for regional and
local flow by using well records to calculate the hydraulic gradient The results
are shown in Tables 4.1 and 4.2. The groundwater flow gradients were calculated
using the formula i=dh/dl. Regionally, two gradients were calculated for
southeasterly flow. The gradients were in the range of 2.1 x 10" to 6.8 x 10" .
3
T A B L E 4.1 R E G I O N A L
FLOW
3
DATA
DATE
LOCATION
HYDRAULIC
H E A D (m)
GRADIENT
Aug/77
1350 Tracey St
30988-8th Ave.
2292 Queen St
46.3
46.0
52.1
2.1 x 10"
2.1 x 10"
Jan/80
Dec/79
Oct/79
31474-8th Ave.
1219-320th SL
1222- 314th SL
42.4
41.2
47.6
6.8 x 10"
6.8 X 10"
FLOW
(m/s)
3
3
RATE
7
7
Figure
4.7
Regional Groundwater Flow D i r e c t i o n
Figure 4.8
GROUNDWATER FLOW DIRECTIONS
\
\
O
51
T A B L E 4.2 PIEZOMETER F L O W
DATA
DATE
LOCATION
HYDRAULIC
H E A D (m)
GRADIENT
FLOW
(m/s)
July 30/82
PI
P2
P3
48.69
47.75
48.52
1.6 x 10-
1.6 X 10"
D e c 14/82
PI
P2
P3
48.76
47.54
48.22
2.3 x 10-
2.3 X 10-
The southwesterly
2
2
RATE
6
4
flow gradients from the piezometers were calculated to be
higher than the southeasterly
flow gradients with the range of 1.6 x 10" to 2.3
1
x 10- .
2
The hydraulic conductivity, K, of the area was calculated using grain size
analysis of di!" cuttings from the installation of the piezometer. The average
hydraulic conductivity value calculated was 1 x 10" m/s indicating that the soil
4
is very permeable.
Groundwater flow rates were then calculated for the regional and local
flows with Darcy's Law, v = Ki, using the data calculated for the hydraulic
conductivity and flow gradients. For the southeast portion of the Upland, the
flow rates were calculated to be 2.1 x 10" to 6.8 x 10' m/s. Using data from
7
7
the piezometers the flow rates were estimated at 1.6 x 10'' to 2.3 x 10" m/s
6
for the southwest flow towards Fishtrap Creek. Therefore, the groundwater flow
rate was higher locally towards Fishtrap Creek than regionally by approximately
two orders of magnitude.
4.3.2 G R O U N D W A T E R
CHEMISTRY
The groundwater in the upper zone of an aquifer of a large sedimentary
basin can be described
as being characterized by active groundwater flushing
through relatively well leached rocks. Water in this zone has calcium (Ca *) and
2
bicarbonate (HCO ) as the dominant cation and anion and is low in Total
3-
Dissolved Solids (TDS)
(Domenico, 1972). The
groundwater in the study area can
be described as an upper zone aquifer and is characterized as a
calcium-magnesium-bicarbonate water. (Appendix
The
C)
previous excellent water in this area has in recent years been
stressed by man's activities which have caused local degradation of water quality.
Contaminants presently known in the groundwater include nitrates, pesticides and
fire retardants.
In 1982, the Upper Fraser Valley Health Unit surveyed the wells in the
area surrounding the Airport to determine
the drinking water. It was
the level of nitrate/nitrite- nitogen in
found that twenty-three of the forty-four wells
sampled were above the acceptable limit of 10 mg/i
highest being 31.0 mg/1.
in Appendix C. The
The
nitrate-nitrogen, with the
distribution of the levels of nitrate/nitrite is shown
high groundwater nitrate values can be attributed to manure
stockpiling, fertilizers, sewage effluent and high permeability of the surficial
geological materials.
In 1984,- a N H R I survey of domestic and industrial wells in the study
area indicated that 9 of the 21 well sampled were contaminated
1.2- dichloropropane (Liebscher, 1985). The
with
active ingredient of this pesticide is
1.3- dichloropropene, and it is used as a soil fumicant on a variety of crops for
nematode and disease control. The
presence of 1,2-dichloropropane
can be used
as an indication of other types of pesticide contamination in the groundwater.
Other pesticides with similar or greater residual properties and solubilities are
likely to be contaminating the area. Also, pesticides with less residual properties
and solubilities are likely to be found in these groundwaters.
Fire retardants from the activities of the Abbotsford Airport effect the
groundwater quality. The major contaminants
of the fire retardants are
ammonium-nitrogen, nitrate-nitrogen, and phosphate.
4.4 CLIMATIC INFLUENCE QN HYDROLOGY
The hydrogeologic behavior of the ditch, stream and groundwater are related to the
seasonal variation of precipitation. The Pacific Climate Region can be generally
characterized as having warm, rainy winters and relatively cool, dry summers. During
the winter a fairly steady succession of low pressure systems moving eastward from the
Pacific Ocean produce very cloudy and rainy conditions. In the summer, frequent long
periods of sunny weather extend over the coast due to high pressure cells.
Temperatures are warm and rainfall is low. (Hare and Thomas, 1979) The climate data
for the Abbotsford Airport .s shown in Table 4.1.
T A B L E 4.1 A B B O T S F O R D AIRPORT
MONTH
AVE. TEMP. ( C)
a
JANUARY
FEBRUARY
MARCH
APRIL
MAY
JUNE
JULY
AUGUST
SEPTEMBER
OCTOBER
NOVEMBER
DECEMBER
CLIMATE
DATA
AVE. PPT. (MM)
1.3
4.2
5.6
8.6
12.2
14.9
16.9
16.7
14.4
10.1
5.7
3.1
207.3
163.8
145.0
104.1
72.9
59.9
37.8
49.0
86.0
170.4
190.5
215.1
The recharge of the aquifer is provided primarily by the late fall and winter
precipitation. The average annual precipitation of 150 cm provides each square
kilometer approximately 1,500,000 m
J
of water annually, most of which
(80%) occurs
between October and April. During this period losses through evaporation and
transpiration are minimal insuring most of the precipitation will go to recharging the
54
aquifer (B.C. Water Supply, 1971). The Upland is not dissected by stream channels
indicating minimal surface runoff, therefore, a significant portion of the precipitation
penetrates into the aquifer. Fishtrap Creek also recharges the aquifer in the winter
months and there is also the possibility of recharge from irrigational practices during
the summer months, although there is no evidence to date to support this source of
recharge. The water table in the aquifer fluctuates seasonally by approximately 3 m.
Low
levels occur in October and November which rebound to high levels in March
and April due to the heavy recharge during the winter months. This is illustrated by
the average monthly water table level of an observation well at the Abbotsford Airport
in Figure 4.9.
The changes in local groundwater flow direction (Figure 4.8) and an increase in
flow rates (Table 4.2) are related to fluctuations in the groundwater levels and can be
explained by the increase in precipitation. The daily precipitation at the / imort during
the study period is shown in Figure 4.10. During the late fall and early winter
months the groundwater level is at its lowest (Figure 4.9) yet rainfall is at its peak
(Figure 4.10). The increase in stormwater runoff increases the amount of discharge to
the ditch causing the groundwater to be recharged locally in the area around the
ditch. Therefore, the hydraulic head in the piezometer closest to the iitch (PI)
increases while the other piezometers in other locations decrease causing a change in
flow direction, gradient and flow rates.
In Fishtrap Creek the discharge was also related to the seasonal variation in
precipitation. The discharge changed from very low flow, almost stagnant in places,
during the summer months to high flows, causing flooding in places, during the stormy
winter months. During the winter months at times of heavy precipitation which cause
flooding, the groundwater-stream water interaction called bank storage could occur. This
interaction moderates the flood wave and causes infiltration into the groundwater for a
period of time (Todd, 1955). This would result in short term recharge of the aquifer
Figure 4.9
Average Monthly Water Table Level 1966 -
Figure 4.10
D A I L Y
i»
5
SEPTEMBER
12
P R E C I P I T A T I O N
19
26
1
OCTOBER
10
17
A T
A B B O T S F O R D
24
I
S
NOVEMBER
1983
D A T E
IS
21
2t
A I R P O R T
4
DECEMBER
1}
20
17
1
JANUARY
1984
57
around the stream banks. The stream was not gauged during the study period,
although it was apparent that the hydrology of Fishtrap Creek was closely related to
precipitation.
The intended purpose of the ditch was to receive storm water runoff from the
runways. The volume of discharge into the ditch changes seasonally in relation to
precipitation. During the summer months, the water level remains static in the first
half of the ditch, decreasing due to infiltration and evaporation and increasing due to
precipitation. During the first storm events, in the fall, when there was considerable
precipitation, runoff water started to flow into tho second half of the ditch. The
runoff water did not reach the stream because of very rapid infiltration into the
ground due to unsaturated conditions and high hydraulic conductivity. Only after
considerable precipitation over a long period of time was there flow into the creek
from the ditch in the early winter months. It took 10 hours during one' of the first
major storms in the winter to have flow from the ditch to the stream Only at the
end of the winter was there any standing water in the second half of the ditch. This
is due to the saturation of the soil and the increase in the water table level. The
relationships between the water environments and precipitation is shown in Figure 4.11.
F i g u r e 4.11
W i n t e r Storm S c e n a r i o
Precipitation
causes
increased
flow
Stream
summer
recharges
aqui fer
Groundwater
winter
intensive
winter storms
carries
pol1utants
through
storm sewers
itch
58
4.5 L A N D IJSF.
In the area encompassing the study area the land use is primarily agricultural.
The
various types of land uses situated around Fishtrap Creek are mainly extensive
field crops and animal husbandry with intensive poultry and animal husbandry included
to a lesser extent (Central Fraser Valley Regional District, 1980). (Figure 4.12)
The
various types of land uses in this area are important to consider when
determining the effect of fire retardant contamination on the various water uses. The
areas of extensive field crops utilize irrigation to nourish their crops during dry
summers and there is use of the groundwater for nourishing liieir livestock. The
degradation of the water quality by sources other than fire retardant waste should be
noted. The land use of field crops degrades the groundwater locally due to fertilization
(Adams, 1982) and pesticide application (Liebscher, 1985). Also, intensive poultry and
animal husbanoiy fiirms cause water quality problems due to nitrogen input to aquatic
environments. The extent of these problems has been discussed earlier.
(Adapted from C. F.V.R.D., 1980)
Chapter 5
RESULTS AND DISCUSSION
5.1 ASSESSMENT OF WATER DATA
5.1.1 I N T R O D U C T I O N
Assessment of the water data involved synthesis of various elements
influencing the distribution of the fire retardant components in the environment
The elements included the chemical and physical nature of the fire retardant,
quantity of aircraft washed, quantity and duration of rainfall, and the
hydrogeological conditions of the area.
The
fire retardant used, PhosChek XB, was analyzed first to identify
parameters which would indicate its presence in the environment In Table 5.1,
the
results on the analysis of the dry powder and of a 2000 ppm solution of
PhosChek X B indicated that ammonium and phosphate were the key parameters.
Potassium and nitrate were also considered to be important parameters due to
the
chemical and physical nature of the ammonium component in soil.
T A B L E 5.1 C H E M I C A L D A T A O F P H O S C H E K X B
PARAMETER
D R Y P O W D E R (ppm)
S O L U T I O N (ppm)
515000
248000
6390
5450
1670
743
625
327
167.
0.40
1.90
1.10
7.40
1.97
0.13
.045
P 0 (mg/1)
NH.-N (mg/1)
N O j - N (mg/1)
Fe (mg/1)
Ca (mg/1)
Mg (mg/1)
Na (mg/1)
K (mg/1)
Cr (mg/1)
4
In order to assess the impact of the aircraft washing on the aquatic
environment, the dates and quantities of the aircraft cleaning activities were
60
61
recorded (Table 5.2) Due to a low fire season and change in management
practices regarding aircraft washing, the number of planes washed out at the
Airport was very low in 1983. Any pollution observed during the study period
indicated
a low level of impact resulting from washing activities in comparison to
previous years. The washing of aircraft was concentrated in October with the
period of time from early October until approximately December considered as
peak conditions when the retardant waste was considered to be washed through
the drainage and hydrological systems.
T A B L E 5.2 A I R C R A F T C L E A N I N G
DATA
DATE
NO. A I R C R A F T
CLEANED
DATE OF NEXT
RAINFALL
D A T E OF N E X T
SAMPLING
August 9
September 27
October 4
October 5
October 6
December 14
1
1
2
1
1 (outside only)
1 (inside only)
August 9
October 2
October 16
October 16
October 16
December 2
• August 10
September 28
October 12
October 12
October 12
December
14/January 12
Precipitation was very important in assessing the impact of fire retardant
waste on the environment The event dates and sampling dates are indicated in
Figure 5.1 in relation to the daily precipitation from August to January.
Precipitation affected the flow of the stream, the washing of the fire retardant
into the ditch, the flow of the ditch to the stream and the groundwater level.
The
effect of precipitation is explained more fully in Chapter 4.
The
ditch, stream and groundwater were assessed separately in order to
identify events of fire retardant contamination. Background and peak flow
conditions were analyzed to determine the temporal and spatial patterns in each
environment of the fire retardant contamination.
Figure 5.1
D A I L Y
P R E C I P I T A T I O N
A T
A B B O T S F O R D
A I R P O R T
70-i
S= sampling date
E- event date
63
5.1.2 P I T C H
WATER
Due to seasonal variation in precipitation as seen in Figure 5.1,
background levels of the parameters varied in the ditch water. In the summer,
the water was relatively static with rainfall events causing dilution of the water.
In the winter months, water flowed through the ditch to the stream during
heavy precipitation events resulting in dilution of the ditch water. The dynamics
of the composition of the ditch water over time is shown in Table 5.3.
T A B L E 5.3 C H E M I C A L D A T A OF T H E D I T C H W A T E R
PARAMEIER
August 3
pH
Specific Cond.
N 0 - N (mg/1)
N H - N (mg/1)
PO, (mg/1)
Fe (mg/1)
Mg (mg/1)
Ca (mg/1)
Na (mg/1)
K (mg/1)
Cr (ppb)
3
4
6.84
225.
1.46
-
y.,5
0.90
1.41
2.04
7.1
2.25
-
DATE
August 31
January 12
March 6
7.04
27.5
0.12
0.89
1.39
0.15
0.47
4.1
3.2
0.69
80.0
6.44
39.9
2.92
0.95
.20
0.0
0.18
6.5
1.46
0.52
85.5'
6.91
37.0
0.09
0.02
.07
0.11
0.20
5.1
1.25
0.29
4.2
Static conditions are shown in the August 3 sampling date when
compared to the August 31 sampling which occurred after a rainfall event show
a substantial decrease in the parameters' concentrations after the rainfall event
Other sampling dates shown were during the winter months with further
reduction in concentration due to the seasonal precipitation events.
The
magnitude of the washing events varied according to precipitation at
the time. The highest measured impact on the ditch water during the sampling
period occurred on October 12 after 5 aircraft were cleaned; no precipitation had
occurred between the time of cleaning and sampling.
The
first storm event took place from October 19 to 23 during which
time an automatic sampling unit collected water samples in the ditch. The
64
drainage system was flushed of the fire retardant waste during this storm. Figure
5.3 shows the rainfall data and Figure 5.2 the ammonium-nitrogen and
phosphorus concentrations during this event Sampling started at 1100 hr October
19 (0 hr) and ended at 1400 hr October 23. The samples taken showed an
increase in most of the parameters except phosphate. The behavior of phosphate
was due to either missing the first phosphate flush or the phosphates were held
back in the drainage system and therefore took longer to flush through the
drainage system. The decrease in the concentration of the parameters from
3000hr
to 3200hr could have either been due to dilution caused by precipitation or
rapid infiltration of the components into the soil. There were also several other
flushes during this time which indicating that the residuals from the fire
retardants required a large amount of rainfall to be completely flushed through
the
drainage system
In another event on December 04, 1983 a plane containing waste
retardant was emptied at the washup area, the waste took approximately three
hours to reach the ditch from the washup area. The impact on the ditch water
is shown in Table 5.4 indicating a substantial increase in the specific
conductance, ammonium-nitrogen, phosphorus, chromium and sodium parameters.
T A B L E 5.4 I M P A C T O F W A S H I N G O N D I T C H
PARAMETER
pH
Specific ConcL(ug/cm)
N O j - N (mg/1)
NH;-N (mg/1)
PO; (mg/1)
Fe (mg/1)
Ca (mg/1)
M g (mg/1)
Na (mg/1)
K. (mg/1)
Cr (ppb)
3
WATER
BEFORE
AFTER
6.25
27.
0.50
0.44
0.478
0.10
0.28
5.1
0.89
0.50
2.8
6.64
1070.
0.34
125.5
51.7
0.15
5.53
16.7
13.5
3.70
252.5
F i g u r e 5.2
N I T R O G E N
A N D
4 - 1 —
P H O S P H O R U S L E V E L S
—
D U R I N G
F I R S T
S T O R M
. •
E V E N T
Figure 5.3
HOURLY PRECIPITATION - OCTOBER 19-23, 1983
200 - i
150E
E
c
'a.
o
o_
50-
0
.a
0
20
4
I
40
60
Hour
JL
80
100
a*
67
5.1.3
STREAM
Due
WATER
to the seasonal nature of stream water chemistry, the sampling
location above the point where the ditch enters the stream was used for
background conditions against the other two sampling locations downstream from
the ditch. Peaks identified in each parameter
that occurred at all three stream
locations were used in analyzing for trends in background conditions. Most of the
peaks which occurred at all three locations occurred during peak flow conditions
in the stream. (See Table 5.5,
TABLE
5.5
Appendix E)
S T R E A M W A T E R CHEMISTRY
PEAKS
PARAMETER
DATE
N H ; (mg/1)
PO}' (mg/1)
Fe (mg/1)
Mg (mg/1)
Ca (mg/1)
Na (mg/1)
K (mg/1)
Cr (ppb)
October 20, 22, 23
November 16, December 14
October 23, December 14
October 12, December 02
October 12, December 02, January 16
October 12, December 02
October 20,22,23
September 28, October 20, 22, 23,
November 16, December 02
In order to determine the impact on the stream from the activities at
the airport, peaks that occurred only in the locations downstream from the point
at which the ditch enters the stream were identified. (Table 5.6)
listed in Table 5.6
The parameters
were the principle components of PhosChek XB. In order to
determine if the peaks were due to PhosChek X B contamination, the dates were
related to events in the ditch.
T A B L E 5.6 D O W N S T R E A M
PARAMETER
NO,
NH,
PO,
PEAKS
DATE
• October 12, December 02
November 16
November 16 .
The
dates of the various peaks in the stream in Table 5.3 showed no
correspondence to events in the ditch. The trend of nitrate-nitrogen
in the
stream water (Figure 5.4) indicated high background levels in the locations
downstream from the ditch which were not significantly different from those
observed on October 12 or December 2. Also, on October 12 there was no flow
from the ditch to the stream. Therefore, the peaks observed for nitrate-nitrogen
in Table 5.3 cannot be attributed to fire retardant contarriination and was
probably contributed by other sources downstream
The
November 16 peaks of phosphate and ammonium- nitrogen in Table
5.3 may have been' due to ditch water input because at this time the ditch
flowed through to the stream But, ammonium and phosphate .oncentrations in
the stream water showed high variability over time. The peaks indicated
in Table
5.3 were probably not due to input from the ditch. Also, dil:->n of the ditch
:
water due to the high stream flow on November 16 would reduce the
concentrations to much lower levels than indicated. Therefore, there is a greater
probability that ammonium and phosphate were contributed by other sources
downstream and not from the fire retardant waste.
To measure the impact the ditch water has on the stream a 72 hour
event was monitored with water samples taken at the point in the ditch before
the ditch entered the stream during a storm event The results showed all
parameters except ammonium were higher in the stream than the ditch. Total
phosphorus concentrations were very similar in both waters ranging from 0.09
mg/1 in the stream to 0.06 - 0.08 mg/1 in the ditch. The ammonium in the
stream varied from 0.0 to 0.02 mg/1 and in the ditch from 0.0 to 0.07 mg/1.
(Figure 5.8) Heavy steady precipitation was needed to have ditch flow through to
the stream. When precipitation decreased the stream water was able to backflow
into the ditch due to decreased volumes and velocities from the ditch. The
Figure 5.4
NITRATE-NITROGEN TREND IN STREAM WATER
6-,
.
Figure 5.5
AMMONIUM-NITROGEN TREND IN STREAM WATER
0.8
T
_
_
Ortho Phosphate (mg/1)
XL
*
Figure 5.7
HOURLY PRECIPITATION - NOVEMBER 14-16, 1983
120
-i
100-
Hour
IN}
Figure 5.8
NITROGEN AND PHOSPHORUS LEVELS DURING NOVEMBER STORM EVENT
O.IO
T
nitrate values during the sampling period showed this occurrence when it
increased to concentrations observed in the stream water during a lull in the
storm (Figure 5.9) The parameters of PhosChek X B showed a possibility of
impacting the stream due to direct flow from the ditch to the stream, but
during the event that was monitored the impact was not significant
5.1.4 GROT INDWATHR
Groundwater
background levels were taken August 31, January 14 and
March 6 sampling dates. There were no significant differences observed in the
background concentration between the groundwater locations for iron,
ortho-phosphate, ammonium, magnesium and pH. There were significant
differences in the background conditions for nitrate-nitrogen, calcium, potassium,
and chromium. (Appendix E)
To determine the spatial difference in the groundwater chemistry a
correlation analysis was performed on the data set from August 31, 1983 to
January 12, 1985. According to this analysis nitrate-nitrogen, ammonium, and
ortho-phosphate were not correlated in three locations at the R=.01 level.
Potassium is only related for P I venus P3 at the R = .01 level. It was
interesting to note that total phosphorus was related at the R=.01 level but
ortho-phosphate was not The parameters that were not correlated were used to
detennine spatial differences over time and to identify events during the sampling
period. (See Figure 3.2 for piezometer locations)
The trend of nitrate values over time in the different groundwater
locations is shown in Figure 5.10. The background trend of nitrate showed that
P2 and P3 were similar with P I having slightly higher background levels in the
spring. The trends of P2 and P3 over time were similar and P I was
significantly different The trend in concentrations was usually PI >
P3 > P2.
All of the locations were significantly different from each other from September
28 to December 15. The piezometer closest to the ditch, PI, showed a sharp
increase during peak conditions in mid October and remained high until mid
November. Depthwise in PI the lower piezometer showed a slight time lag
behind the upper piezometer in nitrate concentration. Therefore, PI showed an
impact of nitrate that can be related to the activities at the airport
Ammonium background concentrations showed a great deal of variation
between each piezometer location and within each piezometer depth. (Figure 5.11)
The peaks also varied in magnitude
between the depths and location. There was
no significant difference from October 12 to November 16 between locations.
Therefore, the distribution of the ammonium from the ditcl. was very difficult to
identify in the groundwater due to natural variability and low concentrations
which were at the lower limit of detection for the method used.
The ortho-phosphate concentrations at different locations all had a similar
trend, but were different in magnitude. In October the trend was PI >
P2. This trend changed from November to December to P2 >
P3
>
P3 > PI.
(Figure 5.12) A l l locations showed evidence of increased ortho-phosphate
concentration at various times which may
or may not j e linked to an event
Most of the concentrations of ortho-phosphate in the groundwater were at the
lower end of the detection limit for the method used.
The trend of potassium i n the groundwater over time and space is shown
in Figure 5.13. From October to December the trend showed PI >
P2 >
P3.
The trend of potassium varied with depth in P2 with an increase in P2A and
P2B from October to December as compared to a relatively stable P2C during
the same period. PI and P3 were always significantly different for potassium and
PI and P2 were the least times significantly different. Even though PI and P3
were always significantly different they were highly corelated for potassium The
Figure 5.9
N I T R A T E - N I T R O G E N
T R E N D
D U R I N G
N O V E M B E R
3-1
~r-
i
1
r
20
2b
30
35
TIME (hours)
r
40
S T O R M
E V E N T
Figure 5.10
NITRATE-NITROGEN TREND IN GROUNDWATER
5T
_
Legend
A
P1A
X
P2A
• P3A
JAN
1984
DATE
APR
—i
i
F i g u r e 5.11
AMMONIUM-NITROGEN TREND IN GROUNDWATER
0.20
Legend
A P1A
X
P2A
• P3A
10
17 24 li
AUG
1983
7 14 21 2 8 5
SEP
OCT
12 19 26 2
NOV
9
16 2 3 JO 7 14 2 1 2 8 4
DEC
>
JAN
1984
DATE
II
18 2 5 I
FEB
8
IS 2 2 2 9 7
MAR
Figure 5.12
PHOSPHORUS TREND IN GROUNDWATER
CD
J ,
_c
Q_
in
O
_c
Q_
O
Legend
O
A P1A_
•
JAN
1984
DATE
APR
P3A
Figure 5.14
NITRATE-NITROGEN TREND IN GROUNDWATER
AUG
1983
SEP
OCT
NOV
DEC
DATE
JAN
1984
FEB
MAR
APR
impact from ammonium in the fire retardant waste which exchanges with
potassium in the soil was difficult to determine because P2, which is the furthest
piezometer from the ditch showed similar trends as PI.
In the groundwater, a nitrate plume from the ditch along the flowline
was indicated. An increase in nitrate-nitrogen concentrations was recorded in P2B
from December to March. (Figure 5.14) At the same time nitrogen concentrations
decreased in all other piezometers including P2A
and P2C. This could be part of
a plume due to the peak of nitrate values noted in PI in late October. This
cannot be substantiated without further reseach.
5.1.5 MUT.TTVARTATF. C L U S T E R
ANALYSTS
Hierarchical grouping analysis was performed on the data set to determine
'spatially and temporally the impact on the environment due to fire retardant
waste. It was also used to determine critical parameters to distinguish between
environments and to determine parameters that would be useful in monitoring for
fire retardant pollution.
The program C G R O U P used each sampling location for each date as an
item and each parameter measured as a key. It compared a series of items over
a series of parameters and stepwise associated them into groups until all the
items had been classified into one or the other of two groups. Items were
grouped in such a way
the
as to rninimize the increase in overall variation within
group. The individual samples were classified in terms of their overall
similarity in twelve chemical properties.
In the grouping analysis performed on the data set a groundwater section
emerged that contained several groups. The component analysis of the
groundwater data involved six distinct groups. The spatial components of the six
groundwater clusters is shown in Table 5.7.
83
T A B L E 5.7 C O M P O N E N T S O F G R O U N D W A T E R
CLUSTERS
GROUP
COMPONENTS
NO. O F SAMPLES
1
2
3
4
5
6
50% P3, 44% PI
100% P3
100% PI
33% PI, 3 3 % P2, 3 3 % P3
84% P2
57% P2, 4 3 % P I
18
15
7
8
25
7
In analyzing the differences between the parameters in the six groups,
Group 3 was significantly different than all other groups except for Group 1 in
most of the parameters. Group 1 and 5 had the least significant differences
between their parameters and therefore were very similar. The temporal
components of the groups showed that Groups 1 and 5 consisted mainly of pre
and post impact dates and can be considered to represent background conditions.
Group 3 consisted of data from P I from October 12 to November 16, the
period of peak flow conditions.
It was determined that Group 3 showed a significant impact from ditch
water that can be related to fire retardant waste.
The parameters which would be useful in momtoring
for fire retardant
waste contamination were parameters of Group 3 which had a unique significant
difference from all other groups. These parameters were specific conductance,
nitrate-nitrogen, and potassium.
5.2 RFLATTONSHTPS B E T W E E N WATER
The
OUAI.TTY A N D P O L L U T A N T
DISCHARGE
distribution of the contaminants was determined by examining the
relationships between the different water environments over time. Background
relationships were first established between the ditch, stream, and groundwater
environments. Then during peak flow conditions the relationships between the various
environments was examined further to determine the impact and distribution of the
84
contaminants with respect to space and time.
5.2.1 B A C K G R O U N D R FT ATTONSHTPS
Background conditions were established using sampling dates before the
fall washing of the aircraft and after the contaminants had passed through the
system in January and March. Background conditions of the ditch water, stream
water and groundwater varied according to the location. The ditch water was
generally significantly different from the stream and groundwater for
rutrate-nitrogen, phosphorus and chromium. The stream water was significantly
different from the other two environments for magnesium, calcium, sodium,
potassium and specific conductance. The groundwater differed from the other two
environments in only pH. A l l the environments were not significantly different
from each otfcs... for ammonium-nitrogen. The parameters of particular concern
1
for detection of fire retardant contamination were nitrate, phosphorus, potassium
and possibly chromium and were assessed further to determine their impact on
the various waters involved.
In the ditch water, nitrate was significantly different than the groundwater
and stream water except on January 12 when the ditch was flowing to the
stream The ditch water concentration for nitrate was usually very low around .5
mg/1. The groundwater concentration range for nitrate was .8 to 2.9 mg/1 with
PI
greater than P3 and P2. In the stream it ranged from 1.0 to 5.5 mg/1 with
higher concentrations at the downstream locations, S2 and S3.
The potential influence of nitrates from the ditch on the stream and
groundwater during background dates was unlikely because the nitrate
concentration was usually significantly lower. Also, the stream and groundwater
concentrations were not significantly different from each other.
35
Ammonium- nitrogen was not significantly different between the
environments on August 31 and March 6. But the ditch water was significantly
different on January 12 than the stream water and groundwater. Therefore, there
was a slight possibility of the ditch water ammonium influencing
the stream and
groundwater.
Due
to dilution from precipitation in the winter, the background
concentration of ortho-phosphate in the ditch was higher in August than in
January and March. The groundwater was usually very low and below the
detection limit. The background concentration of the stream water was relatively
steady at .10 to .20
mg/1.
Background concentrations of. potassium were very similar in the
groundwater and the ditch water with the stream water being significantly higher.
Chromium background concentration varied seasonally between each
environment The ditch water concentrations were higher than the stream water
and groundwater except in January where there was no siginificant difference.
5.2.2 P E A K F L O W
CONDITIONS
During peak flow conditions from October 20 to December 12, the
concentration and distribution of the fire retardant components within
and
between the various environments were examined.
Nitrate concentrations during this time in the ditch remained low and the
stream and groundwater were not significantiy different during this time and were
both significantly higher than the ditch water.
Ammonium distribution from fire retardant waste in the ditch to the
stream and groundwater was difficult to establish. The
ditch was significantly
higher than the stream water from October 12 to October 23 and December 14.
In the ditch the largest peak occurred on October 12, but at this time there
86
was
no ditch flow through to the stream. On November 16, when flow through
occurred there was no significant difference between the ditch and the stream.
The
ditch water concentration at this time was .02 to .11 mg/1 ammonium and
in the stream was .03 mg/1 above the point of input and .10 to .12 mg/1
downstream from the input The source of the increase in the stream could
possibly be from the ditch, but since the concentrations were similar and dilution
would have occurred in the stream, there were likely other sources of ammonium
entering the stream. Ammonium from the ditch did not show a significant impact
on the groundwater. This was probably due to the conversion of ammonium to
nitrate and adsorption of ammonium by the soil.
The
stream and groundwater had ammonium peaks occuring at the same
time, but the stream concentration was greater and significantly different from the
groundwater during peiik flow periods. Therefore, the \;toundwater would not
effect ammonium in stream water.
Pollution due to ammonium in the ditch which is oxidized to nitrate
could effect groundwater and stream water quality. This possibility was also
examined In the stream water it was difficult to detect this conversion because
when the ammonium levels were high in the dixh there was no flow through
to the stream, then when flow through occurred, the ammonium concentration in
the ditch was lower than the nitrate concentration in the stream.
The
conversion of ammonium-nitrogen in the groundwater was easily
detected in the piezometer closest to the ditch where the nitrate concentration
rose in the fall and peaked from mid October to mid November. In the ditch
the highest level of ammonium was recorded on October 12 and then decreased
with increasing precipitation. The ammonium level in the ditch and nitrate trend
in PI is shown in Figure 5.15.
A m m o n i u m - N i t r o g e n (mg/1)
Z.8
88
Phosphorus contamination of the stream from the ditch water was very
hard to determine due to similar concentrations in both the environments during
flow through from the ditch. When the concentration of phosphorus was very
high in the ditch (144 mg/1) there was no flow through to the stream When
flow through occurred on November 16 the ditch concentration ranged from .184
to .548 mg/1 total phosphorus (.242 to .360 mg/1 ortho-phosphorus). Downstream
from the point of input the concentration ranged from .113 to .488 mg/1 total
phosphorus (.114 to .146 mg/1 ortho-phosphorus). There was no significant
difference
between the ditch and the stream for total phosphorus, therefore, since
the ditch water and stream water were significantly different at all other times
during the peak flow period there could have been some contamination of
phosphorus.
The ditch water and groundwater were at all times significantly different
in phosphorus. The trend of the phosphorus concentration in the groundwater
locations were all similar but varied in magnitude. October was the only time
that the piezometer closest to the ditch, PI, was higher in concentration than the
other two groundwater locations indicating a possibility of contamination from the
ditch.
The stream water was usually higher in phosphorus than in the
groundwater, except August 10, October 12, and November 16 when the
groundwater was higher than the stream water. They were only significantly
different for total phosphorus during times of peak rainfall when the phosphorus
concentration increased in the stream.
There was a possiblity that the ditch water impacted the stream water.
Also, it was very difficult to determine if and when the phosphorus from the
ditch was distributed in the groundwater because of very low concentration and
high variability of phosphorus in the groundwater.
39
As expected, there was no impact of potassium in the stream water from
the ditch water as the concentration of potassium was significantly different and
higher in concentration at all times than in the ditch water.
The ditch water during peak flow conditions was significantly different
and also lower in concentration than the groundwater for potassium. In PI, the
piezometer closest to the ditch, there was an increasing trend after the input of
the fire retardant into the ditch and also during the peak flow period which
decreased substantially by mid December. The increase in potassium in the
groundwater. could have been caused by the exchar^e of ammonium with
potassium in the soil. The other groundwater locations remained relatively steady
during the same period except for P2A and P2B winch also showed an
increasing trend during this time. Therefore, there is a possibility that exchange
of ammonium in the son was not the only cause ol ^creasing potassium
concentration in the groundwater.
5.2.3 MUTTTVARTATF, CT.IISTFR
ANALYSTS
In the grouping analysis of the data set several distinct groups emerged
for the ditch water, groundwater and stream watt,r. The component analysis of
the groups are described spatially in Table 5.8.
T A B L E 5.8 C O M P O N E N T S O F A L L D A T A
CLUSTERS
GROUP
COMPONENTS
NO. O F
1
2
3
4
5
6
Groundwater 57% P3, 37% PI
Groundwater 68% P2, 17% P3
Ditch Water 9 1 %
Stream Water 57% SI, 29% S2
Stream Water 50% SI, 50% S2 & S3
Stream Water 50% S2, 50% S3
40
40
23
7
12
10
SAMPLES
The temporal components of the groundwater groups showed Group 1
consisted mainly of dates before December 12, and Group 2 consisted of
90
background dates. For the stream water, Groups 4 and 6 consisted of background
dates and Group 5 of dates during peak flow conditions from October thru
November.
Groups 1 and 2 were very similar and were significantly different than
all other groups in most parameters, namely specific conductance,
nitrates,
ammonium phosphorus, magnesium, sodium, and calcium Within the stream
water. Groups 4 and 5 were very similar, with significant differences only in
calcium and iron. Group 6 was significandy different from Groups 4 and 5 in a
number of parameters including ortho-phosphates,
calcium magnesium -nd specific
conductance.
The parameters that were determined to distinguish between
environments were specific conductance,
ortho-phosphate,
the
magnesium, and calcium.
The parameters that were determined to be useful in monitoring
effect of fire retardant contamination
were nitrate-nitrogen,
i r the
total phosphorus, and
sodium
5.3 C O L U M N F X P F R TMFNT
The column experiment
was designed to simulate groundwater
input conditions. The two objectives
rate of contaminant
of the contaminant
of the column experiment
during waste
were to determine
transport through the soil column and to determine
the
retention
in the soil column.
The rate of contaminant
transport through the soil column was determined by
measuring the specific conductance at half hour intervals along with measuring
other parameters. In Figure 5.16
starting approximately
various
the specific conductance is shown versus time for the
control and two concentrations of fire retardanL
approximately
the
It shows an. increase in conductance
three hours after application with the peak occurring at
four hours after application, then decreasing
exponentially. The rate of
Figure 5.16
TRANSPORT RATE OF PHOSCHEK XB IN A SOIL COLUMN
200-1
:
-
transport of various other parameters showed a similar pattern but with the higher
concentration of fire retardant solution peaking
slightly before the lower concentration
solution. The rate of transport through the soil coiumn of PhosChek X B
was
calculated to be between three and four hours.
The analysis of the parameter concentrations did not show with any statistical
significance, interactions of the PhosChek X B components with the soil or
transformations of the ammonium to nitrate in the soil column. (Appendix F)
Retention of the various components in the soil showed no significant difference
between ti'.e control and experimental columns or between the higher and lower
concentrations of fire retardant solutions. The percentage of various parameters in the
soil after the application of the fire retardant shows no significant differences between
the control and contaminated soil. (Table 5.9)
T A B L E 5.9 C H E M I C A L D A T A O F
PARAMETER
%Total P
%Cr
%Na
%K
%Fe
%Mg
%Ca
The experimental
SOIL IN C O L U M N S
CONTROL
1000 mg/1
SOLUTION
2000 mg/1
SOLUTION
.2437
.0694
2.277
.579
4.295
1.450
2.530
.2127
.0616
2.440
.599
4.020
1.423
2.464
.2484
.0362
2.351
.557
4.079
1.387
2.514
design was very good but the actual experimentation
produced
several problems which hindered in some ways the significance of the results. Because
of the fast rate of transport through the soil column in the first run, the fire
retardant peak was partially missed. A more definite peak was however, obtained in
the second run which was monitored more frequently at half hour intervals.
The results from the soil chemical analysis may
have been more significant if
a different method was used. The retention capability of the fire retardant in the soil
may
have been determined by measuring the capacity of the soil. The adsorption
93
capacity can be measured by applying a constant concentration of fire retardant and
monitoring the output until such time as the input concentration equals the output
concentration. This method may
also be able to show the transformations of the
components or the exchange of the components in the soil better than the method
used.
The
1.
conclusions that were drawn from the column experiment were:
The rate of transport through the soil column of PhosChek XB
was between 3 to
4 hours.
2.
The
fire retardant at the concentration used was leached thru the soil and were
nor retained in any significant quanities.
5.4 P I T C H
SEDIMENT
Sediment and overlying water samples were taken . from the ditch after the fire
retardant was deposited in the ditch and again at the end of the winter in March.
This was to determine the influence of the fire retardant waste has on the ditch
sediment and water and to determine if the chemistry changes over time, particularly,
after a rainy winter with outflow to the stream from the ditch.
Results from sediment analysis of two different sampling dates showed no
significant differences over time in any of the parameters measured. (Table 5.10)
The
overlying water was significantly different over time in all parameters measured except
calcium and chromium.
The
the
results from the sediment analysis suggests that the adsorption capacity of
sediments may
have been reached and that new
in the sediments and may
inputs of waste are not retained
leach to a lower soil profile and/or to the groundwater.
Also, it suggested that the sediment was not flushed through to the stream in
significant quantities.
94-
T A B L E 5.10 C H E M I C A L D A T A O F
PARAMETER
%Total P (ix)
November 2, 1983
1.066
0.635-L540
.1063
0.625-1.539
1.465
1.141-1.798
.452
0.436-0.470
3.797
3.459-4.229
1.138
1.083-1.232
2.172
1.977-2.541
(ranae)
%Na
%Fe
%Mg
%Ca
DITCH
SEDIMENTS
March 6,1984
1.150
0.865-1.475
.1568
0.1115-0.3006
1.234
0.813-1.420
.429
0.368-0.498
3.739
3.208-4.180
1.086
0.964-1.131
1.862
1.193-2.299
The interaction between the sediments and overlying water suggest they do not
influence each other over time. Further research such as desorption studies are needed
to make any conclusive statements.
It was observed that the sediment in the first half of the ditch contained a
thick sludge of fire retardant waste. Due to the thickening agent in PhosChek XB,
this sludge seemed to act as a clay and thus created a low permeable layer in the
area of the ditch closest to the drainage outfall. This would explain the presence of
water' in the first half of the ditch during the summer when hydrologically the water
should have rapidly infiltrated into the soil.
5.5
S U M M A R Y
The amount and frequency of fire retardant waste discharge was directly related
to the operational practices of Connair. In 1983, the number of aircraft cleaned at the
Airport was significantly lower than in previous years due to the low fire season and
the change in washing policy. Yet a significantly measured impact on the groundwater
of increased nitrate-nitrogen concentrations was-observed in the piezometer 11.4 m
from the ditch. The frequency of the fire retardant waste discharge to the ditch was
95
related to aircraft washing and also to major storm events occurring after aircraft
washing.
The major factors which affected the distribution of the contaminants in the
environment were hydrological. Direct infiltration of contaminants into the groundwater
was due to the high hydraulic conductivity of the soil and in part the physical design
of the ditch. The high rainfall during the winter months was directly related to
groundwater flow directions and water table levels, which in turn affected the
distribution of the contaminants in the groundwater. Water transport from the ditch to
the stream was restricted to specif): hydrological events. The
frequency of flow
was
related to the intensity and duration of precipitation events, as was the flushing of fire
retardant waste out of the drainage system. Sediment transport from the ditch was not
observed, therefore, the contaminants were either remaining in the ditch or infiltrating
into the soil and groundwater.
The
rate of transport of the contaminants was rapid, with detection in the
groundwater 11.4 m
from the ditch within a day. The- soil column experiment
demonstrated leaching of the fire retardant within three to four hours after application.
The
critical parameters determined to monitor fire retardant contamination were
specific conductance, nitrate-nitrogen, ammonium-nitrogen, phosphorus, and potassium
Chapter 6
MANAGEMENT
IMPLICATIONS
6.1 INTRODUCTION
In order to effectively manage our resources we must put our scientific
observations within the context of an institutional framework. This would include
legislative Acts for water quality control and agencies which are given the power to
enforce the regulations of such Acts. Water quality standards developed by these
agencies are also included in this framework.
In this chapter, legislative and administrative framework used in controlling
water pollution is discussed with reference to the water quality problem at the
Abbotsford Airport Water quality standards are compared to the water quality results
obtained in this study in order to assess the impact the practice of washing out fire
retardant waste has on the hydrologic environment
6.2 LEGIST ATTVF F R A M E W O R K
The
British
North
America
the division of power between
specific provisions in the
British
Art.
1867 (now the
Consrinnion
Act
1982) defines
the federal and provincial governments. There are no
North
America
Act
1867 at either level of
government
in the area of water resources management In Section 108, the federal
government
gained jurisdiction over navigation and shipping, the sea coast, international
and interprovincial rivers and the fisheries.
Section 109 gave the provinces jurisdiction over the allocation of water uses
within its boundaries and in Section 92A, the ownership of its natural resources which
include forests, minerals, oil and gas.
96
97
by sorption mechanisms.
Adsorption onto hydrous oxides of iron and aluminum is a major component in
phosphate removal. The mechanism involves the retention of P by iron hydrous oxide
surfaces by a ligand exchange
between - O H }
or
=OH.
The type of soil is important for its capacity to adsorb, but sorption is also
dependent on the concentration of P in the solution, the soil p H , temperature,
total
amount of P added and the concentration of various other constituents in the solution
that can react with P or influence soil properties such as pH and redox cycles (US
EPA, 1977).
The mechanism that is considered to be controlling the adsorption-desorption
reaction rate is the mass transfer of P between the soil solution and the soil particle
surface (Shaw et aL, 1975). In general, as solution pH increases, the amount of P
sorbed per unit weight of soil decreases (Ryden et aL, 1977a). As the ionic strength
increases in the solution, the sorption of P increases. The sorption of P tends to be
greater for solutions containing Ca * than those containing Na* (Ryden et al., 1977b).
:
1982).
The major Provincial Acts important to this study are the Waste Management
Act and the Health Act In the context of this study Section 3 of the Waste
Management
Art prohibits anyone from discharging, or permitting the discharge of any
waste material into surface water or groundwater unless they have a permit or
approval of the Waste Management Branch. In the Health Act Section 5, Regulations
41, 42, 43 deal with the distance wells must be located from possible sources of
contamination.
Federally, there are two major legislative Acts and a treaty that deal with
water quality management The Canada WateT Act 1970
enables the federal government
to create water management areas with provincial agreement and also develop national
water quality standards. The key to its effectiveness is the cooperation between the two
98
levels of government because the constitutional position of the Act is unclear.
Consequently, this Act is a rather weak instrument in controlling water pollution.
The
which was
major federal Act used to control water pollution is the Fisheries Act
amended in 1977 and is now
Canada. The
the most powerful environmental Act in
most important clause for pollution control is contained in Section 33(2)
which prohibits the deposit of a deleterious substance in waters frequented by fish or
in any place where the substance could enter such waters. In Section 33(11) a
deleterious substance is defined as:
"any substance that, i f added to any water, would
degrade or alter or form part of a process of degradation or alteration of the quality
of that water so that it is rendered or is likely to be rendered deleterious to fish or
fish habitat or to the use by man of fish that frequent that water"
A
list of Canadian
environmental legislation can be found in Appendix
Abbotsford Airport is located appoximately 2 km
D.
north of the U.S. border.
Therefore, due to its close proximity to the United States as well as the net southerly
direction of regional groundwater and surficial water flow it was
international environmental legislation. The
necessary to examine
Boundary Waters Treaty of 1909
was
designed to prevent and settle disputes regarding the use of boundary waters between
Canada and the United States. The
Boundary Waters Treaty enables international water
quality problems to be jointly studied by both countries.
6.3 ADMINISTRATIVE F R A M E W O R K
The
administrative basis for controlling water pollution in British Columbia is
found in two key Acts, the provincial Waste Management Act and the federal
Fisheries Act A
general schematic diagram showing various environmental agencies
along with their major tasks is shown in Figure 6.1.
Provincially the primary responsibility in water pollution control lies with the
Waste Management Branch in the Environmental Management Division within the
Ministry of Environment
The
stated goal of the Waste Management Branch is to
Figure 6.1 WATER QUALITY CONTROL
MINISTRY OF ENVIRONMENT
Environmental Appeal Board
Waste Management Branch
7
B.C. Dept.
of Health
Regional Districts
and
Municipalities
ENVIRONMENT
CANAOA
i
Industry •
International
Joint
Commission
Inland Waters
Directorate
Environmental
> Protection
Service
Set StandardsMonitor
Enforce
Review
(Adapted from Vancouver Board of Trade, 1974)
100
manage the discharge of waste material from municipal or industrial sources for the
protection of the environment and conservation of the resources (B.C. Ministry of
Environment, 1983). Their program
Management Act.
The
Environmental
is based on the mandate from the Waste
Management Act
and
the Lifter
Art
Water Management Branch of the Planning and Resource Management
Division is another agency involved in water quality management Their stated goal is
to manage the water resources of British Columbia so that the greatest economic,
social and recreational benefits can be realized by its residents through reduced
flooding, and a supply c? w^ter that is plentiful and of good quality.
Water quality standards for receiving water axe established by the Waste
Management Branch which also regulates waste discharges and enforces water quality
standards. A l l waste discharges must be permitted; this includes waste discharges into
groundwater.
The water quality standards for potable water are established and enforced by
the Ministry of Health with assistance from the Water Management Branch whereby
the Public Health Engineering Section gives technical assistance to the Ministry of
Health. This includes groundwater supplies for potable water.
Monitoring of water quality is performed by the Waste Management Branch,
Water Management Branch, municipalities. Regional Districts, and by industry when
directed to do so. Monitoring involves both groundwater and surficial water. If any
governmental agency finds unacceptable levels while monitoring water quality and if it
is close to a water supply the Health Department
is notified.
Environment Canada is the federal agency which is responsible for administering
the pollution control provisions of the Fisheries Act Within Environment Canada, the
Environmental Protection Service investigates threats and adverse impacts on the
environment They enforce the environmental regulations under the Fisheries Act It is
primarily a regulatory agency which implements the national effluent discharge
101
regulations for various industries. The Environmental Protection Service monitors inland
waters and waters inhabited by fish.
The
Environmental
Conservation Service is another agency wherein
Waters Directorate manages the transboundary
the Inland
waters between the provinces and sets
water quality standards for these boundary waters and monitors the water quality at
the border of transboundary
rivers with major concerns. (Environment
Canada, 1982)
Due to the international nature of the waters in the study area, it is necessary
to consider the Boundary Waters Treaty of 1909. Under this Treaty the International
Joint Commission (IJC) was established far international water disputes as a permanent
unitary body. The UC's responsibilities under the Treaty include the responsibility to
investigate specuic water related problems when requested by either or both the
governments called a Reference. Recommendations made in a Reference are not
mandatory to e i ^ T government unless they are made under Article X which are
binding. Article X has never been used to date. (UC, 1982) The Boundary Waters
Treaty does not specifically deal with groundwater. To date the IJC has not had any
cases involving groundwater and therefore, there are no precedents set in this area.
Within the context of this study, the Abbotsford Airport is federally-owned
land and is therefore a 'gray' area in environmental management The province has no
jurisdiction over waste discharges at the Airport even i f the discharge enters provincial
lands. Enforcement and monitoring of waste discharges is therefore handled
Environmental
by the
Protection Service (EPS). EPS can apply for a waste discharge permit
from the province if it feels it is necessary.
The
U C would become involved in this water quality problem only if requested
by either or both governments. It is uncertain if a groundwater quality problem would
to receive any action due to the definition of water in the treaty which does not
include groundwater. But Article EX states that "any other questions or matters of
difference arising between them., along the common frontier...shall be referrecl..to UC".
102
This is a very general article; most references have been made under Article IX and
this is probably wheie a groundwater issue would be dealt with.
6.4 WATFR
QUALITY
STANDARDS
Water quality standards can be examined along with the results obtained in this
study to determine the magnitude of pollution caused by fire retardant waste. Standards
may take the form of ambient or effluent discharge standards. Ambient standards are
based on biological, chemical and physical properties of the receiving waters. It uses
the assimilative properties of the receiving waters. Effluent diiJiarge standards specify
the type and amount of waste which can be disharged into the water environment
(McPhee, 1978) Other important definitions are:
Objectives: Desirable levels of water quality to be obtained in either short-term
or long-term water resources management programs.
Standards: Legally prescribed limits of pollution and/or deterioration which are
established under statutory authority.
Criteria: Scientific requirements upon which a decision or judgement may be
based concerning the suitability of water quality for the preservation of the
aquatic environment and/or to support designated use(s). Criteria are descriptive
expressions of the effects that are known or expected to occur whenever or
wherever a detrimental factor and/or pollutant reaches or exceeds a specific level
for a specific time.
In Table 6.1 the maximum water quality results from this fixe retardant study
axe compared to guidelines for the various water uses.
According to the guidelines for the protection of livestock and irrigation of
acidic soils, the water quality results obtained in the study area were well within their
limits. The only exception to this was the chromium results from the ditch water
which exceeded both guidelines. The distance to an area where irrigation is utilized,
very low concentrations in the groundwater, and the physical and chemical nature of
TABLE 6.1 MAXIMUM MATER QUALITY RESULTS AND GUIDELINES
Parameter*
Stream
Ditch
Groundwater
Drinking Water*
6.12
2.60
4.91
6.5
N0 -N
5.02
2.92
5.19
10.0
NH -N
0.74
.146
25.6
0.5
144.
0.16
.136
.488
1.85
150.
1.25
.400
0.25
0.2
6.2
2.87
1.82
pH
3
4
4
Total P
P0
Fe
Mg
Ca
21.0
10,1
Na
20.0
4.05
17.3
K
Cr
.051
2.82
1.130
10.6
3.06
0.^5
.0239
6.5 - 9.0
0.2
0.3
150.
500.
.05
0.02
-
7
0.05
0.3
-
3
Livestock
_
100.
c
6
200.
2
Freshwater Aquatic Life
•
8
Irrigation''
4.5 - 9.0
-
-
-
-
-
-
-
LE 1000.
LE 50.
-
-
-
-
-
-
-
.100
LE 1.0
LE .1
t
„Recommended Standard for Drinking Water - B.C. Health
-Guidelines for the Protection of Freshwater Aquatic Life - U.S. EPA, 1976
^Guidelines for Livestock and Wildlife Watering, Environmental Studies Board, U.S. EPA, 1973
^Guidelines for Irrigation of Acidic Soils/Continuous Use ( A l l S o i l s ) , Ontario, EWS Board, 1973
gMinimuin Recorded oH values.
^Form not indicated.
•Unionized form.
gLee, G.F. et a l . , 1979.
Units in mq/1 exceot DU.
104
cfarornium causes the concern to be insignificant This also applies to the case for
livestock drinking water.
According to the recommended drinking water standards, the groundwater quality
was unacceptable during the study period. The
pH
of the groundwater went as low as
4.91 and at no time was it ever near the level recommended by B.C. Health. Yet the
criteria given by EPA
(1976) of a pH
of 5 - 9 puts the concentrations observed
within the range for domestic water supplies for the majority of the study period. The
main reason B.C. Health has a pH
of 6.5 as a standard is in consideration of
treatment processes utilized for water. This is not a relevant consider~*'on in the
Abbotsford Airport region dne to the use of well water for their domestic water
supplies. Therefore, the pH
The
value is acceptable.
total phosphorus concentration was over the recommended standard by
double the value in the piezometer closest to the ditch on August 31, 1^83
the groundwater samples were above the .2 mg/1
1983 sampling date. Ortho-phosphate
P0
4
Most of
standard before the October 20,
concentrations during the same period of time
were well below the standard.
There were several areas of concern for freshwater aquatic life according to the
water quality data collected during the study period. When examining the stream water
quality the ammonium-nitrogen, total phosphorus, and iron concentrations were above
recommmended levels and the pH
was below recommended levels. The
groundwater
which recharges the stream showed unacceptable values for pH, ammonium-nitrogen,
and total phosphorus. The possibility of the ditch water entering the stream causes
concern when examining the pH
value, and ammonium-nitrogen, total phosphorus, iron
and chromium concentrations.
The pH
values observed in the stream were all within the guideline limits of
6.5 to 9.0 except for those recorded on January 12, 1984. The
lower pH
value could
have been due to a variety of causes including instrumental error of the pH
meter.
105
The pH
value in the ditch was extremely low in October at one sampling site.
During this time there was no flow through to the stream. The pH
of the ditch
water usually ranged between 5.5 and 7.1. In a review by Doudoroff and Katz (1950)
it was stated and is still valid that,
"It appears that, under otherwise favorable conditions, pH values above 5.0
and ranging upward to pH 9.0, at least, are not lethal for most fully
developed freshwater fishes. Much more extreme pH values, perhaps below
4.0 and well above 10.0, also can be tolerated indefinitely by resistant
species."
The pH
values of the groundwater ranged from 4.91 to 6.03. The low
pH
values were obtained from the piezometers during the first storm event involving heavy
precipitation at the Airport. The pH
values were at the low end of the range but
according to Doudoroff and Katz (1950) it appears that there was no serious threat to
fish at that time, but may
still be a threat to other forms of aquatic life such as
the organisms that the fish eat and effect' other life history stages.
The main reason of a criteria of .05 mg/1
of phosphorus for streams is to
prevent the development of biological problems and to control eutrophication (US
EPA,
1976). This reasoning has been disputed due to the many exceptions to the
relationships that one cannot reliably predict water quality problems due to algae, based
on phosphorus concentrations at one time during the year (Lee et al, 1979). It is
therefore difficult to assess the effect of phosphorus on the stream due to either the
ditch or the groundwater since they were only slightly above the disputed level of .05
mg/1
phosphorus. But, a ditch water concentration of over 1.0 mg/1
most certainly one of 144. mg/1
phosphorus and
would create problems in the stream. During the
period of high phosphorus concentrations in the ditch, there was no flow through to
the stream and by the time there was flow through the concentrations of phosphorus
were greatly reduced to acceptable levels in the ditch.
The highest ammonium nitrogen concentration in the stream (0.74 mg/1)
converted to the unionized ammonia form was only .0067 mg/1
when
ammonia nitrogen
106
which was under the limit of .02 mg/1 unionized ammonia. The next highest
concentration was .29 mg/1 ammonium-nitrogen and when converted was well under
the guideline for unionized. For the groundwater after conversion of the highest level
of N-NFL the result was also well under the guideline given.
In the ditch, though, the highest unionized ammonia-nitrogen concentration was
.133 mg/1 which is extremely high and very toxic to freshwater aquatic life.
Fortunately, the period of high concentrations of ammonium occured when there was
no flow • through to the stream waters. During flow through, the highest
ammonium- nitrogen concentration was .478 mg/1 which when converted to unionized
ammonia was 6.5 x 10" mg/1 and well under the limit for unionized ammonia.
4
The
safe concentration for iron is 0.3 mg/1 for freshwater aquatic life. The
stream water is higher than this limit at 1.85 mg/1 at the highest recorded
conc^sTation. The sampling
location above the ditch was over this criteria at a i i times
except once when it was .28 mg/1 Fe. One process that iron can be released into the
water is by the lowering of the redox potential due to an input of organic matter or
the input of other types of reducing materials. (Smith et al., 1979) The stream was
turbid during the period of extremely high iron concentrations. Iron concentrations at
the other two sampling
locations were much less. Yet, there were still periods when
both locations were over the recommended limit of -.3 mg/1 Fe.
The
high concentrations of iron were not related to the fixe retaxdant waste
problem as the stream had inherent high concentrations of iron before it reached the
ditch input The ditch only exceeds the limit a few times and during these times
there is no flow to the stream.
The
chromium guideline of .100 mg/1 as Cr was not exceeded in the
groundwater or in the stream In the ditch, the chromium concentrations were
exceedingly high. Levels recorded would have been extremely toxic to freshwater
aquatic life i f the ditch was discharging into the stream Again, this was not the case,
107
by the time when the ditch was discharging into the stream the concentration of
chromium had lowered to acceptable levels.
6.5 S U M M A R Y
The
- M A N A G E M E N T IMPLICATIONS
major legislative Act that would be used to control the waste discharge at
the airport is the federal Fisheries A c t Section 33(2). Since the waste is being
discharged onto federal lands, EPS is responsible for the environmental
management of
any wastes. The provincial Waste Management Branch has no jurisdiction on federal
lands, therefore, mur~ rely on EPS to enforce the water quality standards.
The
UC, also, will not become involved with this pollution problem unless the
waste produces unaccep cable conditions in Fishtrap Creek and is requested
by one or
both governments to study the problem. Also, at this time it is uncertain as to the
extent of U C involvenr-'iff in a transboundary groundwater pollution problem.
In examining the water quality standards, the results obtained during the study
period show no immediate threat to drinking water supplies, irrigational water uses or
livestock water. There are problems with various parameters which threaten
freshwater
aquatic life. In particular there are high concentrations of chromium, ammonia, iron
and phosphorus in the ditch which could enter the stream water. When high
concentrations occurred in these parameters during the study period there was no direct
flow from the ditch to the stream. But, when flow does occur there is a likelihood
that a slug of material that was residing in the ditch could be flushed into the
stream (that is if it did not infiltrate into the groundwater during this period). The
stream already has a problem of high iron concentrations which could be a threat to
freshwater aquatic life.
Chapter 7
CONCLUSIONS AND
RF.COMMFNDATTONS
7.1 C O N C L U S I O N S
In studying the effects of forest fire retardant waste at Abbotsford Airport the
following conclusions can be drawn from the results:
1.
The critical parameters indicating pollution by the fire retardant PhosChek X B
were ammonium-nitrogen,
nitrate-nitrogen, and phosphorus. In the groundwater
the Titical parameters also include potassium and specific conductance. Specific
conductance, phosphorus, magnesium and calcium were found to be useful
parameters, distinguishing between diicii, stream and groundwater environments. The
critical parameters which could cause groundwater supplies to become toxic are
nitrate .litrogen, chromium, and phosphorus. The critical parameters which could
cause stream water toxicity were ammonium-nitrogen,
phosphorus, iron and
chromium.
2.
The response time of fixe retardant contaminaton was rapid due to the high
hydraulic conductivity of the soil. Fixe retardant pollution was detected by an
increase in nitrate-nitrogen concentration within one day in the groundwater. The
rate of contaminant transport in the sediment column experiment was within
three to four hours after application of the fire retardant
3.
Components of the fire retardant waste were detected spatially in the
groundwater. The transformation of ammonium to nitrate was the major indication
of pollution. The fixe retardant leached from the ditch and impacted the
groundwatex during peak flow periods 11.4 m from the ditch. Also, high nitrate
108
109
concentrations were detected at least 3 months after the peak flow periods
m
from the ditch. The
77.8
stream seemed to be unaffected by the fire retardant
waste during the study period, therefore, the distribution of fire retardant
contaminants could not be followed.
4.
The
overall impact of the fire retardant waste pollution at the
Abbotsford
Airport at this time is not serious. In relation to the pollution already existant
in the area due
to fertilization practices and poultry farming, the pollution
due
to nitrate-nitrogen from fire retardant waste at the Airport is not a serious
threat The
During
impact will certainly depend upon the number of aircraft washed.
the study period due
to a low fire season and a policy change on
washing practices only a fraction of the fleet was
entire fleet was
washed at Abbotsford. If the
washed at the Airport the potential for impact on
the
environment would increase quite substantially.
5.
The
management of the waste discharge is the responsibility of EPS
waste is discharged onto federal lands. The
because the
major legislative Act that is used to
control the waste discharge at the Airport is the federal Fisheries Act Section
33(2).
110
7.2
1.
RFCOMMFNPATTONS.
Other contaminants from aircraft cleaning activities should be investigated, in
particular, the cleaning agent Voxal, which contains anionic surfactants.
2.
An expanded
laboratory study involving a greater concentration of PhosChek
XB
using the method for adsorption capacity to determine the capacity of the soil to
adsorb and leach the constituents of the fire retardant should be made.
1.
The operation of washing out aircraft at the Abbotsford
Airport should be
restricted until further studies on groundwater contarnination can be done.
2.
For further studies into fire retardant waste discharge at Abbotsford
following aspects should be
a.
Airport the
considered:
During the first storm event of the season after aircraft have
been washed monitor the groundwater as well as the stream
water continuously.
b.
Water table levels should be checked continously to get a
better idea of the dynamics between the ditch and groundwater.
c.
Column and/or batch leaching tests on the sediment from the
ditch to determine the solubility and leachability of the
components in the sediment
d.
The groundwater should be monitored at frequent intervals.
Long term monitoring of the groundwater for nitrate pollution
should be done to establish the direction and rate of nitrate
transport
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APPFNDTX A - USF OF CHFMTCAT. FTRF R F T A R D A N T S TN C A N A D A
Use of Chemical Fire Retardants in Canada
Gallons
1982
Province
(Source:
NRC,
Retardant Used
1983
0
0
0
0
199,830
0
0
0
193,600
1,433,065
6,785,&£4
10,110
17,184 hi.
Newfoundland
P.EJ.
Nova Scoria
New Brunswick
New Brunswick
Quebec
Ontario
Manitoba
Saskatchewan
Alberta
British Columbia
Yukon
NWT
Of
1984)
117
0
0
0
0
118,705 (534,173)
0
0
0
160,000 (727,360)
377,475 (1,716,001)
3,727,000 1
8,337
1,003,698 1
FOREST FIRE FLAME-INHIBITING (LONG-TERM) RETARDANTS USED IN CANADA
Brand name
Fire-Trol 100
Composition
Percentage
A m m o n i u m sulphate
(NH
),S0
4
65.6
(21-0-0)
4
Attapulgite d a y thickener
Fire-Trol 931-L
(Source: Lieskovsky
and Newstead, 1980)
32.8
Iron o x i d e coloring
1.1
Corrosion inhibitor
0.5
A m m o n i u m phosphate
93.0
( A l l i e d A P P 10-34-0)
A t t a p u l g i t e clay thickener
and color
Fire-Trol 931
APS
4.0
carrier
Iron oxide coloring
1.5
Corrosion inhibitor
1.5
A m m o n i u m phosphate
(MAP-DAP
93.0
suspension
9.4-32.4-0)
A t t a p u l g i t e clay
and color
thickener
Iron oxide coloring
1.5
Corrosion inhibitor
1.5
Guar gum thickener
Fire-Trol 934
4.0
carrier
Ammonium
(liquid)
phosphate
variable (0.5 _ . * % b y
volume)
97.72
(Allied A P P 10-34-0)
Fire-Trol 936
Corrosion inhibitor
1.50
Wetting agent
0.78
A l l c h a r a c t e r i s t i c s as i n F i r e - T r o l 9 3 4 w i t h e x c e p t i o n o f 0 . 1 0 % b i o d e g r a d a b l e
97.62% ammonium
Phos-Chek X B
phosphate
M o n o a m m o n i u m phosphate
NH H P0
4
2
89.0
(U-55-0-)
4
Guar gum thickener
7.0
Iron oxide coloring
2.0
Corrosion inhibitors and
2.0
stabilizers
Phos-Chek X B - H
M o n o a m m o n i u m phosphate
NH H P0
4
2
92.0
(11-55-0)
4
Guar g u m thickener
4.5
Iron o x i d e coloring
1.5
Corrosion inhibitors and
2.0
stabilizers
Phos-Chek 259
D i a m m o n i u m phosphate
(NH J HP0
4
2
4
92.5
(21-53-0)
Guar g u m thickener
2.5
Iron o x i d e coloring
1.0
Corrosion inhibitors and
4.0
stabilizers
118
d y e and
APPENDIX
R - SUBSURFACE
Airport
Test
Holes
Well
Well
No.
1
2>
2B
3
Date
Drilled
Static
1970
1942
3.6
1970
1942
0.0.61
Level
DATA
Log
Depth
(m)
Information
Description
Materials
or
0.0-1.2
Silly
sandy
gravel
1.2-3.0
Clean
sandy
dense
gravel
sandy
dense
gravel
3.0- 5.5
Clean
5.5- 7.6
Gravelly
7.6- 15.2
Sandy
0.0-4.6
Hard
packed
4.6- 5.1
Grey
clay
5.1- 8.2
Coarse
sand
clay
sand
Grey
clay
0.0-1.7
Silty
sandy
1.7- 4.6
Clean
4.6-6.6
Gravelly
dense
6.6- 9.1
Sandy
Gravelly
12.2- 13.7
Sandy
and gravel
and gravel
wb.
gravel
dense
9.1-12.2
Clay
coarse
gravel
82-238
0.0-1.5
clean
sandy
gravel
sand
gravel
sand
gravel
loam
1.5-5.5
Dirty
coarse
5.5-5.7
Hard
clay
5.7- 11.3
W b . coarse
11.3- 12.2
Clay
&
122-13.7
Grey
clay
sand
&
sand
gravel
&
and
boulders
sand
&
gravel
hardpan
gravel
\
Domestic
Date
Drilled
Sialic
level
Water
Wells
Depth
Well
Nov.
Oct
Aug.
July
June
1976
1981
1977
1971
1980
15.2
9.1
6.1
10.7
4.6
(m)
Description
of
Materials
L o g Information
0.0-5.8
Till
5.8-10.0
Sandy
clay
100-15.2
Brown
sand
15.2- 16.8
D r y sand
168-20 1
Till
20.1-21.0
Coarse
&
gravel
(clayey)
sand. wb.
21.0-
Blue
clay
0.0-9.7
Sand
&
gravel
9.7-107
Tine
sand
10.7- 23.3
Silly
clay
23.3- 23.8
Fine
brown
sand
23.8- 25.0
Fine
brown
sand
25.0- 29.6
Clay
29.6- 31.1
line
sand
0.0-5.2
O l d well
5.2-16.8
Fine
16.8-18.3
Sill
sand,
0.0-13.7
D u g well
13.7- 1 4 6
Gravel
146-21.3
Clay
213-29.6
llardpan
29 6-31.1
Sand
31.1- 33.0
Gravel
0.0-13.7
Gravel
&
some
sand
gravel
Domestic
Well N o .
Date
Drilled
Static
Level
Water
Wells
Depth
Well
July
11
12
13
1.3
May
1976
5.1
Oct
1979
10.2
Mar.
10
1979
May
Feb.
Jan.
Sept.
1979
1980
1979
1979
1970
12.2
9.1
12.8
17.7
15.7
(m)
Description
of
Materials
L o g Information
13.7-16.1
Drown
16.1-20.3
Fine
black
sand
20.3-20.4
Blue
clay
sand
0.0-4.6
Dry
gravel
4.6-7.6
Wb.
gravel
7.6-9.1
Fine
brown
0.0-14.2
Sand
&
sand
gravel
0.0-9.1
Existing
9.1-11.6
Packed
11.6-18.3
Wb.
0.0-12.2
Sand
&
gravel
12.2-34.1
Sand
&
gravel
0.0-9.1
tiled
sand
sand
well
&
&
gravel
gravel
Gravel
9.1-18.3
Wb.
sand
well
0.0-13.1
Old
13.1-29.9
Sand
0.0-24.1
Old
24.1-24.8
Sand
0.0-9.1
Sand,
9.1-13.7
Compact
&
a n d gravel
gravel
Novak
gravel,
well
cobbles
gravel
i
ro
Domestic
Well N o .
Date
Drilled
Static
Level
Water
Wells
Depth
Well
13
Dec.
1970
20.3
(m)
log
Description
13.7-168
Sand
168-18.8
Sand,
&
18.8-21.0
Wb.
21.0-22.5
Gravel
0.0-16.8
Open
16.8-28.3
Sand
Sand
sand
85
0.0-18.3
15
May
1978
5.2
0.0-3.1
Sand
3.0-5.8
Gravel
17
18
19
20
May
Oct.
July
June
1974
1977
1971
1974
7.3
13.4
&
&
gravel
sand
&
gravel
gravel
5.8-12.2
Sand
&
0.0-12.8
Sand
SL gravel
12.8-21.3
Pine
sand,
clay
0.0-4.2
Silt,
sand
4.2-11.3
Sand
&
gravel
11.3-13.4
Sand
&
gravel
0.0-9.1
Old
9.1-15.2
Sand
9.1
0.0-13.1
Gravel,
6.1
0.0-1.2
Top
1.2-4.6
Till
9.7
silty
hole
1981
1977
gravel
gravel,
Sept.
Aug.
Materials
information
14
16
of
&
balls
gravel
well
&
soil
gravel
sand
ro
rv>
Domestic
Well N o .
Date
Drilled
Sialic
Level
Water
Wells
Depth
Well
(m)
Log
Description
of
Materials
Information
4.6-7.6
Till
7.6-10.7
Gravel
&
gravel
10.7-17.7
Sand
&
&
till
gravel
21
Oct.
1975
5.0
0.0-9.1
Sand
.
22
Aug
1977
7.6
0.0-7.6
Dug
well
7.6-13.1
Wb.
sand
&
0.0-8.5
Sand
&
gravel
&
gravel
23
24
25
26
27
July
May
Aug.
Mar.
Aug.
1976
1970
5.0
3.5
1977
1979
1979
55
6.6
8.5- 9.6
Sand
9.6- 10.7
Sand
0 0-1.2
Open
1.2-8.0
Sand
gravel
hole
&
gravel
00-58
Dug
well
5.8-12.2
Wb.
sand
0.0-5.5
Gravelly
till
5.5-1.8
Sand
gravel
0.0-4.2
Boulders
4.2-6.6
Dry
gravel
6.6-12.2
Wb.
gravel
&
&
&
gravel
gravel
Municipal
Water
Well
Well 1-og
Date Drilled
Oct. 1974
Static Level
7.0
Depth (m)
Information
Description of Materials
0.0-7.6
Sand &
gravel
7.6-18.3
Sand &
gravel
18.3- 27.4
Sand &
gravel
27.4- 30.5
Fine sand &
30.5- 31.5
Fine sand
31.5-32.0
Clay
32.0-33.5
Sandy clay
gravel
APPENDIX B -
SUBSURFACE
DATA
PIEZOMETER DATA
Piezometer
Elevation (m)
Total Length
(m)
P1A
P1B
51.21
5.49
6.16
0.76
0.46 '
0.69
0.69
P2A
P2B
P2C
49.41
3.47
5.12
5.73
0.55
0.52
C49
0.69
0.55
0.61
P3A
P3B
P3C
51.35
5.30
5.79
6.07
0.55
0.52
0.24
0.64
0.55
0.55
12S
Stick Up
(m)
Screen Length
(m)
APPENDIX C- MATER QUALITY DATA
No
Address
Date
Depth
(m)
pH
Specific
Cond.
NO.,
mg/1
NH
mg/r
4
2
PO
4
mg/r
Fe
mg/1
Ca
mg/1
Mg
mg/1
Na
mg/1
K
mg/1
5.4
16.8
4.5
8.4
2.0
26.8
5.8
5.0
1.8
480 Ross Rd.#2
04/05/79
24.4
8.0
149
.002
-
-
2 480 Ross Rd.#l
04/05/79
18.3
7.6
193
.002
-
-
3 875 P e a r d o n v i l l e
28/08/80
39.6
8.4
2770
.002
-
-
0.15
20.4
16.0
4
1600-312 St.
23/01/75
25.3
6.9
185
7.9
-
-
1.05
22.0
4.9
4.8
4
" Test Well
A f t e r 5 Hrs Pump.
26/03/74
25.3
6.6
167
9.93
< .01
-
ND
20.5
4.1
8.6
-
4
" Test Well
A f t e r 50 Hrs
28/03/74
25.3
6.8
165
10.72
<.01
-
ND
19.7
4.1
8.2
-
5
31890 Marshall Rd
28/05/74
29.0
7.4
155
0.07
<.0l
-
1.98
17.2
5.6
8.2
-
6
31534 King S t .
23/05/74
29.9
6.4
107
6.08
<.01
-
0.05
12.3
3.7
2.6
-
6
31534 King S t .
23/05/74 . 29.9
6.6
108
5.6
<.0l
-
0.05
12.3
3.7
0.07
-
7
1327-320 St.
04/04/74
30.9
7.1
173
1.79
^.01
-
0.10
18.9
6.0
5.8
-
8
31286 King Rd.
08/06/77
21.3
6.5
222
17.4
-
.022
0.05
26.2
2.9
6.9
1.5
1
11.
Non Detectable
''Source: NHRI Groundwater Q u a l i t y Survey Data, Unpublished.
9
1
532.
20.
1.1.
ON
APPENDIX C - WATER QUALITY DATA
N i t r a t e / N i t r i t e Survey^"
No.
Address
Depth of
Well (m)
Nitrate/Nitrate
Nitrogen (mg/1)
1
594 Mt. Lehman Rd.
5.5
13.4
2
29963 Huntingdon Rd.
4.6
13.3
29963 Huntingdon Rd.
3.6
21.2
3
14 Clearbrook Rd.
27.4
0.02
4
31788 Huntingdon Rd.
28.0
0.02
5
321 Harnm Rd.
6
30710 Huntingdon Rd.
27.4
1.68
7
30738 Huntingdon Rd.
18.3
2.22
3
143 Mt. Lehman Rd.
4.6
12.2
9
18 Ross Rd.
4.6
10.1
10
226 Ross Rd.
3.6
14.7
11
598 Ross Rd.
4.6
1.07
12
29749 Huntingdon Rd.
5.5
0.04
13
287 Town!ine Rd.
4.6
16.3
14
1266 Hope Rd.
24.4
11.4
15
595 Mt. Lehman Rd.
5.5
20.8
16
614 Clearbrook Rd.
5.5
17.0
17
31822 Huntingdon Rd.
5.5
21.4
18
32294 Huntingdon Rd.
30.5
26.5
19
266 Ross Rd.
20
339 Townline Rd.
21
30671 Boundary Rd.
1
4.6
5.5
22.8
8.60
29.0
17.4
4.6
12.0
Adams, 1982
127
APPENDIX
D
CANADIAN ENVIRONMENTAL
FEDERAL
LEGISLATION
Arctic Waters Pollution Prevention Act
Atomic Energy Control Act
Boundary Waters Treaty (1909)
Canada Shipping Act (ammended 1971)
Canada Water Act (and Phosphate Regulations)
Canadian Wildlife Act
Canadian National Railway Act
Clean A i r Act
Criminal Code
Department of Transport Act
Dominion Water Power Act
Environmental Comtaminants A a
Fertilizers Act
Fisheries Act
Fisheries Development Act
Food and Drug Act
Forestry Development and Reseach Act
Hazardous Products Act
International River Improvements Act
Migratory Birds Convention Act
Motor Vehicle Safety Act
National Energy Board Act
National Harbours Board Act
National Housing Act
National Transportation Act
Navigable Waters Protection Act
Northern Canada Power Commission Act
Ocean Dumping Control Act
Pest Control Products Act
Pesticide Residue Compensation Act
Plant Quarantine Act
Radiation Emmitting Devices Act
Regional Development Incentives Act
St Lawrence Seaway Authority Act
Territorial Lands Act
Transport Act
Transportation of Dangerous Goods Act
Weather Modification Information Act
LEGISLATION
P R O V I N C I A L (B.C.)
LEGISLATION
Coal Mines Regulation Act
Ecological Reserves Act
Energy Act
Environmental Management Act
Environment and Land Use Act
Fire Services Act
Fisheries Act
Forest Act
Geothermal Resources Act
Health Act
Highway Act
Islands Trust Act
Land Act
Litter Act
Mine Regulation Act
Ministry of the Environment Act
Motor Vehicle Act
Park Act
Petroleum and Natural Gas Act
Pipelines Act
Pharmacy Act
Recreational Land Act
Sewerage Assistance Act
Soil Conservation Act
Water Act
Weather Modification Act
Weed Control Act
Waste Management Act
a
DEFINITION OF SYMBOLS IN .APPENDIX E § F
A.
LOCATIONS
Groundwater Piezometer Locations: PL\
D i t c h Locations:
Stream Locations:
3.
D1A
DIB
DIG
SI
S2
S3
CHFMICAL DATA
p.H
SC
NO3
NH4
0.P04
TP04
Fe
Mg
Ca
Na
K
Cr
PP'i'
pH
S p e c i f i c Conductance (uphrns)
iNitvate-Nitrogen
Ammonium-Nitrogen (mg/1)
Orthophosphate (mg/1)
T o t a l Phosphorus as phosphate (mg/1)
Iron (mg/1)
Magnesium (mg/1)
Calcium (mg/1)
Sodium Qng/1)
Potassium (mg/1)
Chromium (ppb)
P r e c i p i t a t i o n C-l mm)
130
P2A
P2R
P3A
P3C
APPFNDTX
F. -
FTF.TD
STTTDY
CTTF.MTC A I .
DATA
LONG TERM MONITORING WATER DATA
P 1A
DATE
03/08/83
10/08/83
31/08/83
28/09/83
12/10/83
20/10/83
22/10/83
23/10/83
16/ 1 1/83
02/12/83
14/12/83
12/01/84
06/03/84
P1B
DATE
03/08/83
10/08/83
31/08/83
2 8 / 0 9 ".3
12/10/83
20/10/83
22/10/83
23/10/83
16/11/83
02/12/83
14/12/83
12/01/84
06/03/84
P2A
OATE
03/08/83
10/08/83
31/08/83
28/09/83
12/10/83
20/10/83.
22/10/33
23/10/83
16/1 1/83
02/12/83
14/12/83
12/01/84
06/03/84
P2B
DATE
03/08/83
10/08/83
31/08/83
28/09/83
12/10/83
20/10/83
22/10/83
23/10/83
16/ 1 1/83
02/'l2/83
14/12/83
12/01/84
06/03/84
/
pH
5 .62
SC
40. .5
42. ,2
5 .36
56.
53.
5 .39
57.
5 .55
81 .
5 . 47
73.
5 .26
4 .91
75.
67 .
5 .84
5 .40
62.
S . 55 . 55.
5 .05
39. 5
47 .
5 .65
PH
5 .59
5 .50
5 . 30
5 .51
5 . 47
5 . 36
4 .94
5 .78
5 . 66
5 .56
5 .07
5 . 72
sc
47.
44 .3
45 .
56 .
51 .
71 .
70.
68.
65.
63.
54 .
39 .
0P04
.038
.008
0.
0.
.006
.002
0.
.008
.007
.004
0.
0.
.005
TP04
QP04
.059
.086
0.
0.
. J40
.004
0.
.008
.002
.004
0.
0.
.009
TP04
TP04
0.
0.
0.
0.
0.
.05
0.
0.
0.
.04
0.
0.
0P04
.030
.024
0.
0.
.010
.002
0.
.006
.009
0.
0.
0.
0.
NH4
N03
2 .00
1 . 76
0.
1 .70
0.
1 .80
0.
1 .96
0.
1 . 93
0.
2 .06
.02
2.. 20
0.
2 . 26
0.
2 . 10
.01
1 . 98
0.
3. 41
0.
6 . 35
0.
0P04
.087
. 106
.002
.002
.01
.006
.004
.004
.008
.006
0.
0.
.003
TP04
N03
1 .42
1 .56
2 .62
2 .94
4 . 15
4 . 46
4 .71
4 .71
4 . 84
3 .76
3 . 13
2 .56
2 .98
PH
5.. ao
5,.72
5,. 57
5..81
5 . 75
5 . 66
5 .03
5 . 83
6 .00
5.. 17
5 . 34
5 . 88
SC
44
44
39
43
41
53
49
51
46
48
46
47
72
.5
.7
.
.5
.
.
.
.
.5
.
.
.
.
0.
0.
.02
0.
0.
.03
0.
0.
.04
.04
0.
.04
NH4
N03
1 .59
1 .40
0.
2 . 10
0.
.08
3 . 50
3 . 36
.02
3 . 62
0.
4..07
0.
4 .73
0.
5 . 19
0.
4 .04
.03
3 .62
0.
2. 1 1
0.
3 . 25 - .09
SC
N03
38 .5 1 . 33
43 .9 1 . 43
5 .71
35 .5 1 . 34
37 .
1 . 72
5 . 48
33 .5 1 . 54
5 . 80
5 . 7 1 • 44 .5 1 . 65
5 . 59
42 .
1 . 68
1 .62
5 .02
42.
5 .81
36 .5 2 .03
5 . 94
38 .
1 . 42
5 .68
35. 5 1 . 35
5 . 30
26 .5 0 . 33
5 .84
29 . 0 .71
PH
5 .81
NH4
NH4
IT!
.21
.007
. 30
.013
.026
.059
.066
.038
.01
0.
.31
.31
. 36
.013
.019
.050
' .047
.038
0.
0.
. 28
. 28
. 28
.013
.015
.028
.058
.027
0.
0.
. 27
. 27
. 31
.013
.018
.040
. 060
.044
0.
0.
Fe
.06
. 18
. 15
0.
.07
. 12
. 40
0.
0.
0.
0.
0.
0.
Mg
Ca
0 . 74 3 .95
0 . 76 3 . 10
1 . 23 7 . 2
1 .25
7. 6
9. 7
1 .60
1 . 73 10 .0
1 .71
9. 3
1 . 73 9 . 4
1 .80 10 . e
1 . 39 7 . 3
3. 8
0 .98
1 .90
0 .73
0 . 74 3 .52
Na
1 .93
1 .85
2 .80
2 . 30
2 .90
2 . 47
2 . 48
2 .48
. 46
2 .25
1 . 73
1 . 45
1 . 47
K
.65
.72
.95
. 85
.90
.90
. 95
.90
. 85
.90
.61
.56
.51
Cr
Fe
. 25
. 20
.07
0.
.04
0.
0.
0.
0.
0.
0.
Mg
Ca
2 .40
0 .84
3 .05
0 .80
1 .02
6. 5
0 . 95 5 . 7
1 . 18 8 . 4
1 . 52 3 . 7
1 . 54 a.. 6
1 .59
8.. 7
1 .80 10. , 6
1 .31
7 .0
1 .03
4 . 1
0 . 73
1 .90
.
0 . 74 4 .8
K
Na
2 .04 0 . 72
1 . 94 0 . 69
2 . 50 0 .80
2 . lO 0 . 75
2 . 10 0 . 85
2 . 37 0 . 90
2 .52 0 .95
2 .41 0 .90
2 . 47 0 .90
2 . 38 0.. 90
1 .82 0..65
1 . 45 0 . 56
1 . 47 0..51
Cr
o:
0.
Mg
Fe
. 12 0 . 70
. 1 1 0 .68
.05 0 .88
1 .02
0.
.03 0 . 7 1
0.
0 . 82
0.
0 . 84
0 .85
0.
0 . 83
0.
0.
0.. 74
0.
0.. 64
0.. 44
0.
0.. 40
0.
Fe
. 25
. 16
.04
0.
.04
0.
0.
.04
0.
0.
0.
0.
0.
Mg
0..81
0. 82
0.. 72
0.. 70
0. 95
1 .07
.
1 .07
1 .06
1 .2 1
1 .03
0. 82
0. . 98
0 . 73
0
0
0
0
0
0
0
0
0
0
0
0
0
3. 9
3. 5
23 . 9
5. 8
3 .0
2. 3
3. 3
7. 3
1. 4
2. 4
4. 4
4. 5
4
16
16
6
7
4
16
5
2
3
2
3
. 4
. 1
. 9
. 3
. 1
. 9
.5
. 1
. 8
.9
. 9
. 2
Ca
Na
K
Cr
3 . 14
2 .05 0., 72
3 .00
2 ..6
1 . 82 0. 75
4 .5
2 . 20 0. .67
3. 5
6 .5
15 . 9
2 . 20 0..85
5 .2
2 .00 0. 85 ' 14 .8
1 . 88 0. 75
5 .3
3. 2
1 .90 0. 90
5 .2
3. 5
1 . 89 0. 90
4 .5
5 .3
6 .0
1 .81 0. 80
6 .9
4 .7
1 . 86 0. 80
2 .0
1 .5
.
2 .3
1 . 48 0. 63
1 . 40 0. 61
1 .6
2 .1
1 ..19 0. 45
2 .9
2 .6
Ca
Na
K
2 .62
2 .. 10 0. 62
3 .36
2 .07 0. 69
5 .8
2 . 30 0. 75
5 .0
2 .05 0. 70
6 .5
2 .20 0. 30
6 .7
2 . 13 0. 70
6 .5
2 .20 0 . 70
6.6
2 . 13 0. 70
2 . 1 1 0. 75
a. 4
5 .6
2 .12 0. 80
1 .72 o.63
3 .9
1 .80 0 . 69
7 .0
1 .51 0 . 55
4 .0
Cr
3 .0
5 .9
13 .7
5. 3
4 .3
5. 1
3 .7
5.3
0. 6
0. 9
0. 3
0. 5
132
P2C
DATE
03/08/83
10/08/83
31/08/83
28/09/83
12/10/83
20/10/83
22/10/83
23/10/83
16/ 1 1/83
02/12/83
14/12/83
12/01/84
06/03/84
P3A
OATE
03/08/83
10/08/83
31/08/83
28/09/83
12/10/83
20/10/83
22/10/83
23/10/83
16/11/83
02/12/83
14/12/83
12/01/84
06/03/84
P3B
OATE
03/08/83
10/08/83
31/08/83
28/09/83
12/10/83
20/10/83
22/10/83
23/10/83
16/11/83
02/12/83
14/12/83
12/01/84
06/03/84
P3C
DATE
03/08/83
10/08/83
31/08/83
28/09/83
12/10/83
20/10/83
22/10/83
23/10/83
16/11/83
02/12/83
14/12/83
12/01/34
06/03/84
01A
DATE
03/08/83
10/08/83
31/08/83
28/09/83
12/10/83
20/10/83
22/10/83
23/10/83
16/11/83
02/12/83
14/12/83
12/01/84
06/03/84
PH
5 . 82
5 . 77
5 . 54
5 .81
5 .75
5 .65
5 . 17
5 . 80
5 . 92
5 .68
5 . 36
5 .83
PH
5 . 77
5 .69
5 . 53
5 .81
S .80
5 . 76
3 . 37
S .73
5 . 86
5 .77
5 .60
PH
5 . 69
5 . 73
5 .61
5 . 86
5 .80
5 .96
5 . 29
5 .80
5 .87
5 .81
5 .78
PH
5 . 68
5 .83
6 .03
6 .01
5 .81
5 .82 '
5 . 34
3 . 80
5 . 88
5 . 80
5 . 80
PH
6 . 85
6 . 39
5 .89
6 . 30
6 . 26
5 . 63
6 . 77
6 . 28
7 . 10
6 . 68
6 . 82
NH4
0P04
.06 1
.010
.004
0.
.008
.002
.004
.012
.008
.023
0.
0.
.014
TP04
0P04
.079
.002
.058
0.
. 136
.014
.024
.004
.005
.004
0.
0.
TP04
0PO4
.092
. 122
.052
0.
.012
.004
0.
.002
.112
0.
0.
.02
TP04
TP04
0.
.05
.02
0.
0.
.04
.02
0.
.02
.03
.04
0P04
.115
.050
.064
0.
.016
.004
0.
.002
.005
.008
0.
0.
NH4
OP04
TP04
SC
49 .5
50. 2
43.
43. 5
39. 5
51 .5
48.
53. 5
46 .
50.
48 .5
48. 5
50.
N03
1 .80
2 .00
1 .90
2.. 14
2.. 14
1 .97
2..29
2.. 27
2 . 23
2.. 33
2.. 28
2,.62
2.. 12
sc
NH4
N03
2., 70
2..68
0.
1 .96
.
. 16
2.. 78 0.
2..44
0.
2.. 40 0.
2,. 54 0.
2 .65
.
0.
2..58
o:
3 .00
.
0.
2.,55
0.
2., 24 0.
83 .
83.
65.
59.
52.
66 .
60.
61 .
60.
60.
51 .
46 .
sc
81 .
81 .
60.
59 .
52. 5
65 .
6 1 .
59.
58 .
60.
52 .
46 .
sc
82 .
82 .
63 .
60.
52.
66 .
63.
59 .
60.
59
50
47
sc
N03
2 .92
.
2 .79
1 ,oO
2 .71
2 .54
2..41
2 .57
.
3 .06
2 .81
.
2 .96
2 .48
2. 06
N03
2 .72
2 .82
2. 0 0
2. 72
2. 56
2 .48
2 .60
2 .65
2 .70
2 .92
2 . 74
2 . 25
N03
0.
0.
0.
0.
0.
0.
0.
0.
.02
0.
0.
0.
NH4
. 10
0.
.06
0.
0.
0.
0.
0.
0\
.04
0.
NH4
. 32
. 24
. 29
.010
.019
. 031
.054
.076
0.
0.
. .37
.01
. 39
.072
.038
.027
.067
.044
0.
. 40
.06
. 32
.010
.020
.044
.060
.033
0.
K
Na
2 . 20 0. 53
2 .09 0. 56
2 . 30 0. 59
2 .05 0. 60
2 .60 0. 70
2 . 12 0. 60
2 . 14 0. 65
2 . 13 0. 65
2 . 13 0. 65
2 . 16 0. 65
1 .83 0. 53
1 .91 0. 59
1 . 70 0. 49
Cr
4 .38
4 .05
6. 2
6 .3
7 .3
6. 6
7. 1
6. 6
7 .8
5 .9
4 .2
6 .4
5. 4
Mg
Ca
Fe
. 15 1 .81
9. 7
. 15 1 . 70 7 .77
1 .49 10. 2
0.
1 . 40 a.4
0.
.23 1 . 36 8 .6
.06 1 . 48 8 .7
1 .61
9. 9
0
1 . 47 8 .7
0.
1 .56 10. 0
0.
1 . 38 7 .4
0.
3. 9
0 .94
0.
*
.05
6 .1
0.
Na
K
2 .98 0. 73
2 .92 0. 55
2 . 30 0. 76
2 . 60 0. 55
2 .60 0. 65
2 . 59 0. 50
2 . 56 0. 55
2 . 58 0. 55
2 . 54 0. 50
2 .50 0. 55
1 .93 0. 40
1 .92 0. 45
Cr
F e . Mg
Ca
. 15 1 .82
9. 1
. 25 < . 79 7 .3
45
.05
9 .5
1 . 47 • 8.8
0.
.08 1 .31
8 .6
.08 1 . 47 8 .7
.03 1 . 48 9 .0
1 . 45 8 .6
0.
1 . 54 10. 0
0.
1 . 27 7 .0
0.
1 .04
4 .2
0.
5 .9
0.
0 .99
K
Na
3 .06 0. 61
2 . 97 0. 66
3 . 10 0. 58
2 . 70 0. 55
2 . 70 0. 65
2 .59 0. 50
2 . 58 o. 55
2 . 58 0. 55
2 .56 0. 50
2 . 35 0. 55
1 . 97 o. 4 1
1 . 9 0 0. 42
Cr
Mg
Fe
. 12 0 .90
. 10 0 .88
.06 0 .92
0.
0 . 98
.07 1 .09
1 .06
0.
1 .08
0.
.04 1 .06
1 .07
0.
.03 1 .01
0.
0 . 96
1 .01
0.
0.
0 .84
Mg
Fe
. 15 1 .81
. 22 1 . 70
.25 1 .50
.40
1 . 55
. 28 0.
. 39 .05 1 . 29
.026 .08 1 . 48
.016 0.
0 . 63
. 04 1 0.
1 . 48
.040 .06 1 . 56
.049 .04 1 . 34
1 .02
0.
0.
O. o . 99
Fe
Mg
1 . 56 13.6
245
. 70 1 . 26
16.0
34 . 5 0 .05
0.89
1 . 77
4 .00
. 15 0 . 47
225
10.50
. 30 2 . 28
0 . 55 14 . 98 11.8
280
0 . 45 25.6 144 .0
I 5 0 . 0 1 . 182 .87
. 044
27
. 446 . 13 0 . 2 1
0 . 37 0 . 66
.617 . 1 10 . 27
38
0 . 33 0. 79
. 760
41 . 5 0 . 2 1 0. 29
. 591 0.
. 460
0 . 34
. 497 .05 0 . 10
15.
. 242
0 . 20 0.07
27
. 478
.831 . 10 0 . 28
0 . 50 0. 44
27 . 5 0 . 55 0. 98
. 30
0.
0 . 12
. 26
42 . 0 .41
1 .00
.01
0.
0 . 22
61
.119
.65 0 . 57
0 . 13 0. 79
.09
Ca
Ca
9. 1
7 .0
9 .1
9 .2
8 .8
8 .3
4 .2
8 .4
10. 0
7 .0
.
4 .2
5 .7
Ca
4 .40
4 .0
8 .4
10. 1
2 .6
3 .9
4 .3
2 .4
5. 1
3 .6
6 .1
7 .2
K
Na
3 .02 0. 55
3 .01 0. 64
3 . 70 0. 57
2 . 90 0. 53
2 . 70 0. 60
2 .60 0. 55
2 . 60 0. 55
2 . 6 1 0. 50
2 . 57 0. 50
2 . 35 0. 55
1 .95 0. 42
1 . 35 0 .42
Na
8.
3.
13 .
13 .
0.
1.
1.
0.
0.
0.
1.
2.
K
3 .. 4
10 . 1
8. 2
7 .6
5. 2
5.. 2
6. 2
6. 4
0 . 8
1 .8
2 .2
1 .2
3 .1
9..7
17 ,6
8.. 1
5. 6
5.
4 .a
6. 5
0 . 4
2.. 2
3. 2
6 .0
10.. 3
8 .6
10. 2
1 1. 7
4 .5
10. 0
1. 0
1 .
4
2 .8
Cr
3 .2
1 .
9
14 . 1
9 .8
12 .0
5 .7
9 .5
6 .8
0. 9
0. 6
0. 6
Cr
5 2 .02 220 . 8
4 0. 76
33 . 8
5 2 .10 201 . 5
3 2 .00
80 .0
83 0. 35
16 . 7
33 0. 40
23 . 2
49 0. 45
9. 4
26 0. 20
21 9
2. 8
89 0. 50
83 0. 38
3 .. 1
64 .0
49 0. 56
5. 6
20 0. 5 1
133.
D1B
DATE
03/08/83
10/08/83
31/08/83
28/09/83
12/10/83
20/10/83
22/10/83
23/10/83
16/11/83
02/12/83
14/12/83
12/01/84
06/03/84
D1C
DATE
03/08/83
10/08/83
31/08/83
28/09/83
12/10/83
20/10/83
22/10/83
23/10/83
16/11/83
02/12/83
14/12/83
12/01/84
06/03/84
pH
6 .84
7 .04
6 .03
S .95
6 . 19
5 .96
5 .49
6 .60
6 .50
6 .88
6 . 44
6 .91
pH
SC
225 .
218.
2 7 ,, 5
45.
87 ,
26.. 5
25.
29. 2
12.,5
19. 5
22 . 5
3 9 ..9
37 .
SC
NO 3
1 .46
1 .35
0 . 12
0 .57
0 .27
0 .41
0 . 36
0 . 12
0 . 15
0 . 18
0 . 43
2 .92
0 .09
N03
3 4 . 5 0 . 26
.42
. 33
45.
0 . 78
117.
. 33
0 .67
. 6 0 1950.
0 . 48
. 15
21 .
0 . 17
3 7 . 8 0 . 24
.50
1 15 . 0 . 19
.89
. 10
30.
0 .64
S .66
20.
0 .49
5 .68
63.
2 . 73
6 .85
31 .
0 .05
8
6
6
2
6
5
6
6
C 1
O 1
PH
OATE
03/08/83 7 . 1 1
10/08/83
3 1 / 0 8 / 8 3 7 . 14
2 8 / 0 9 / 8 3 6 .88
1 2 / 1 0 / 8 3 6 .90
2 0 / 1 0 / 8 3 6 . 89
2 2 / 1 0 / 8 3 6 .66
2 3 / 1 0 / 8 3 6 .44
1 6 / 1 1 / 8 3 6 . 76
0 2 / 1 2 / 8 3 6 . 88
14/12/83 6 .80
1 2 / 0 1 / 8 4 6 . 28
0 6 / 0 3 / 8 4 6 .92
SC
N03
1 .00
1 15.
146 .
0 .86
1 10.
0 .32
106.
0 . 89
115.
0 .49
93.
0 . 83
107 .
2 .68
1 10.
3 .31
2 . 46
60.
103 .
2 . 45
7 1 . 2 . 35
77 .
2 . 32
89.
1 .. 87
DATE
PH
0 3 / 0 8 / 8 3 6 .85
10/08/83
3 1 / 0 8 / 8 3 6 .85
2 8 / 0 9 / 8 3 6 .'55
1 2 / 1 0 / 8 3 6 .75
2 0 / 1 0 / 8 3 6 . 92
2 2 / 1 0 / 8 3 6 . 75
2 3 / 1 0 / 8 3 6 . 44
1 6 / 1 1 / 8 3 6 .80
0 2 / 1 2 / 8 3 6 .80
1 4 / 1 2 / 8 3 6 .86
1 2 / 0 1 / 8 4 6 . 24
0 6 / 0 3 / 8 4 6 .82
SC
135 .
175 .
135 .
124 .
114.
135 .
98 .
1 10.
74 .
119.
82 .
100.
112.
DATE
03/08/83
10/08/83
31/08/83
28/09/83
12/10/83
20/10/83
22/10/83
23/10/83
16/11/83
02/12/83
14/12/83
12/01/84
06/03/84
pH
SC
.02
. 54
.97
.01
.80
.60
. 73
. 78
. 70
. 12
. 86
185 .
160.
142.
140.
155 .
91 .
121 .
57 .
146 .
90.
117.
136 .
7
6
6
7
6
6
6
6
6
6
6
N03
3.. 39
3 . 72
3 ,60
.
.3 . 79
4 ,. 39
2 . 73
2. 36
3. 31
3 . 74
4 . 29
2 . 97
4 . 22
4 . 50
NO 3
4 .6 0
3 . 70
3 . 48
4 . 46
4 . 19
1 .83
3. 30
2 . 94
5 . 02
3 . 40
4 . 57
4 . 50
0P04
9.75
15 . 2
16.5
1 . 39
0 . 89
1 . 76
. 909
4 .56
3 . 59
.032
0 . 43
.804
0 . 59
.310
0 .05
. 242
0 . 1 1
. 127
0 .07
. 24
0... 73
. 20
0 .95
.070
0 .02
NH4
TP04
Mg
Fe
.90 1 . 4 1
1 . 20 2 .06
1 . 95
. 15 0 . 47
2.00
. 12 0 . 49
4.2
.88 0 .94
. 326 . 3 0 0 . 24
. 779 .07 0 .27
.950 0 .
0 .24
. 548 .06 0 . 10
.03 0 . 19
:
0.
0 .09
0.
0.
0 . 18
. 1 10 . 20
.06
2
NH4
0PO4
0 . 27
1 .72
7..02
0 . 46
0 . 34
0,, 59
0..02
0..04
0 ..88
2 .00
.
0.
2.60
1 .273
4.56
.034
.500
. 536
.36
.058
.21
. 13
.063
NH4
0P04
.080
.020
. 168
.032
.032
.056
. 132
.042
.049
.026
. 17
0.
.021
TP04
0P04
.037
. 026
.016
.010
.012
.030
TP04
0.
0 ., 74
0,.02
0,
0 . 29
0 ..08
0 ..02
0 ..03
0 . 13
0 .. 12
0 . 08
0 . 04
NH4
0.
0.
0.
0.
0.
0 . 10
0 . 02
0 . 12
0. 1 1
0 . 08
0.
0.
NH4
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
04
1 1
10
08
1 1
.042
.114
.027
. 22
0.
.018
0P04
.004
.004
.006
.008
.008
.072
.050
. 146
.017
. 14
0.
.013
9
TP04
Fe
Mg
2 . 60
. 4 0 0 . 64
. 55 0 .51
2. 50
4. 4
1 . 25 1 . 26
. 351 . 15 0 . 19
. 581 .05 0 .27
. 592 0 .
0 . 16
. 184 0 .
0 .06
.113 0 .
0 .60
0.
.08
1 .05
.02
0.
.04
. 12 0 . 15
Ca
2..04
4 .72
4. 1
3. 3
5.. 7
3. 3
4. 1
2 .8
1. 8
4 ., 8
3 .0
.
6., 5
5. 1
Na
7. 1
17 . 3
3 .2
3. 5
7 .7
0 . 88
1 . 30
0 .55
0 . 18
0 .62
0 . 70
1 .46
1 . 25
Ca
Na
K
Cr
2.25
2 . 82 76 . 8
0 . 69
80 .0
0 . 85 1 130.
51 .3
0.55
4 .5
0 . 30
14 . 4
0 . 35
9 .0
0 . 40
15 . 3
0 . 15
3. 4
0 . 35
6. 3
0 . 30
85 . 5
0 . 52
4. 2
0 . 29
K
Cr
4 . 4 . 4 .5
1 . 13
40 . 8
3. 2
2. 8
1 . 10 99 .8
1 1
5 .9
.
. 6
1.10 . 69 .8
13 .6
2. 7
0 .90 0 . 3 0
24 . 4
1 . 40 0 . 45
3. 3
8. 2
2 .6
.
0 . 44 0 . 30
1 .9
8. 1
0 . 16 0 . 10
4 ..9
1. 7
1 . 12 0 . 8 0
3 .9
0 .67 0 . 2 8
2..5
7 .0
1 . 59 1 . 23
2. 5
4 ..0
1 .05 r>. 35
6. 2
K
1 . 76
2 . 80
3.21
. 15
2 .05
3 . 10
3.35
3.75
2 . 35
1 . 80
1 .65
1 . 52
1 . 22
Cr
Mg
3 .88
4. 5
3. 7
3 .50
4 .6
3 . 26
4 .21
3 .53
2 . 23
3 . 14
2. 2
2 . 43
2 . 24
Na
Ca
6 .0
10.. 6
13. 2
12 . 5
6. 8
12. 1
10.. 1 • 5 . 7
13 . 3
9. 5
5. 4
10. 1
6. 1
12. 8
4. 8
10, 3
7 .7
2 . 68
6. 4
9 .8
4 .9
3. 1
7 .8
4 . 15
7 .7
3. 4
Fe
.40
. 32
. 37
. 20
. 27
. 22
.40
. 10
.032 . 35
.
.065 . 47
.088 . 88
. 488 . 52
.094 . 29
. 49
.25
0.
. 36
0.
Mg
5 .00
5. 5
5. 5
4 . 50
5. 1
4 . 83
4 .40
3. 90
2 . 85
3 94
2 . 65
3 . 12
3. 04
K
Ca
Na
Cr
5.. 9
1 . 72
12. 8
7 8
16 . 2
1 . 78
3.. 6
17 . 2
7 . 6 2. 15
8 .5
5 .8
13. 3
1 . 90 13 . 7
6 . 7
4 .6
15 . 8
1 . 90
7 ., 5
14 . 1
6 . 9 2 . 40
14 .0
5 .8
13. 5
3 . 25
1 1 2.
5 .5
4 .05
8 .7
2 . 78 3 .00
9 .1
9.4
1 16 .
1 .1
5 .2
1 . 90
1 .4
3 .4
1 . 65
6. 0
4 . 65 1 . 70
9 .5
3 .6
3 .7
1 . 38
9.8
2 .0
TP04
Mg
Ca
5 ..70 16 . 7
5 .8
19 . 8
6 . 1 18 . 5
4 . 45 14 . 5
6 .2
2 1 0.
5 . 42 17 . 2
5. 07 15 . 7
3 .07
9.4
9 .0
2. 62
4 . 32 14 . 2
7 .0
2 . 87
4 . 28 14 . 3
3 . 3.3 1 1 3.
Fe
1 . 80
1 . 10
. 39 1 . 85
.25
. 68
. 37
. 65
.046 . 78
. 129 . 70
.092 .80
. 308 . 40
.094 . 33
. 36
0.
. 28
. 44
0.
. 36
. 35
. 42
.016
.087
.093
.113
.066
0.
.01
Fe
. 35
. 35
. 35
.48
. 17
. 30
.60
. 75
.61
. 30
. 43
.05
. 38
K
Na
6 .0
1 . 85
7 .6
1 . 85
8 .2
2.21
5 .8
2 . 20
1 . 95
20. 0
7 .2
2 . 10
5 .7
3 . 55
4 .43 3 . 8 0
2 . 77 3 .00
5 .4
1 . 90
3 .5
1 . 65
5 . 20 1 . 70
4 .0
1 . 35
3 .9
8. 6
15 . 3
4. 1
9. 1
19 . 2
3. 1
12 . 7
2. 2
6 .0
2.
. 4
1. 6
Cr
12 . 4
51 . 0
3 .0
25 . 7
8 .9
3 .7
7 .4
1 .
0
4 .6
0. 6
4 .9
134
SHORT TERM MONITORING OF DITCH WATER (OCTOBER 19
TIME
10/19/11 6
10/19/15 6
10/20/08 7
10/20/10 7
10/20/12 7
10/20/14 7
10/20/16 7
10/20/18 7
10/20/20 6
10/20/22 6
10/20/24 6
10/21/02 6
10/21/06 &
10/21/08 6
10/21/10 6
10/21/12 6
10/21/14 6
10/21/18 6
10/21/22 6
10/22/02 6
10/22/06 5
10/22/10 5
10/22/14 5
10/22/16 5
10/22/18 5
10/22/20 5
10/22/22 5
10/22/24 5
10/23/02 5
10/23/04 5
1 0 / 2 3 / 0 6 5.
10/23/08 5
1 0 / 2 3 / 1 0 5.
10/23/12 5
1 0 / 2 3 / 1 4 5.
PH
22
33
06
12
16
20
17
1 1
77
37
99
99
66
61
61
56
45
33
16
26
85
96
95
63
26
22
49
54
51
S3
62
55
60
68
82
sc
62
62
141
148
150
147
136
100
49 5
81
1 16
1 17
50
62
57
49
23
18
18
22
22
23
17
36
26
25
25
25
27
27
27
28
28.
29
30.
5
1
9
1
9
0
9
5
5
5
5
N03
0 61
0 70
0 49
0 41
0 38
0 40
0 34
0 37
0 62
0 39
0 32
0 30
0 40
0. 4 6
0 46
0 31
0 32
0 30
0 25
0 30
0. 16
0 18
0. 19
0 47
0. 5 0
0 25
0. 3 2
0. 32
0. 3 6
0. 2 7
0. 21
0. 19
0. 2 0
0. 2 2
0. 2 5
NH4
1 69
1 76
3 44
3 46
3 50
3 46
3 30
2. 2 6
1 26
2. 0 0
2 94
3 02
1 61
1 72
1 73
0. 7 6
0. 44
0. 27
0. 2 7
0 . 51
0. 6 3
0 70
0. 2 8
0.
0. 3 7
0. 4 0
0. 4 0
0. 4 3
0. 4 7
0. 5 4
0. 5 8
0. 5 9
0. 6 5
0. 6 5
0. 6 6
0P04
1 50
1 46
1 96
1 77
1 81
1 78
1 78
1 31
0 02
1 22
1 73
1 73
0 94
1 08
1 16
1 99
0 37
0 09
0 33
0 52
0 75
0 79
0 20
0 65
0 23
0 15
0 26
0 22
0 33
0 41
0. 5 7
0 51
0. 5 3
0 60
0. 6 4
TP04
1 688
2 168
1 796
1 777
1 759
2 332
2 409
1 020
1 003
1 335
1 976
2. 9 6
1 033
1 108
1 201
2 356
0 380
0 1 14 0
0. 3 6 3 0
0 555 0
0. 7 1 7 0
0
0 69
0. 2 2 2 0
1 393
0. 6 9 0 0
0. 2 4 3 0
0. 2 4 2 0
0. 5 0 0 0
0. 3 7 7 0
0. 4 7 4
0. 6 2 1
0. 5 8 5 0
0. 5 8 8 0
0. 9 7 9 0
0. 5 6 6
FE
13
1 1
13
13
10
12
13
07
06
09
1 1
12
05
08
08
06
03
06
04
03
05
MG
0. 4 9
0. 4 4
3. 4 3
3. 4 4
3. 7 0
3. 7 5
3. 4 6
2. 2 0
0. 7 7
1 .6 6
2. 7 8
2. 8 0
0. 6 5
0. 7 6
0. 8 0
0. 4 0
0. 14
0 . 10
0. 12
0 . 12
0. 15
0. 18
0. 10
0. 3 5
0. 17
0. 18
0. 17
0. 16
0. 19
0. 2 2
0. 2 4
0. 2 6
0. 2 6
0. 2 6
0. 2 8
- 23, 1983)
CA
5 .1
4 6
12 1
12 8
13 0
12 8
1 1 7
9 6
4 9
7 6
10 2
10 3
.4 8
'5 1
'5 2
4 5
2 8
2 0
1 5
2 3
1 8
2 2
1 6
4 6
3 3
3 0
3 0
3 0
3 2
3 3
3 3
3 5
3 4
3 6
3 5
NA
3 44
3 43
8 30
8 80
9 90
9. 0 0
8. 5
6.1
2 38
4 .7 9
7 10
7 10
2. 6 6
3 00
3 1 1
2 17
1 .0 0
0 60
0. 5 3
0. 5 4
0. 5 5
0. 6 6
0. 4 7
1. 6 8
1. 0 6
1. 16
1. 17
1. : J
1. 3 0
1. 36
1. 4 0
1. 4 2
1. 42
1. 4 5
1. 4 9
K
0 70
0 55
1 90
1 60
1 55
1 70
1 50
1 30
0 75
1 15
1 13
1 35
0 75
0 80
0 85
0 65
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
50
35
35
45
40
50
30
45
25
20
20
25
35
40
40
45
45
35
45
CR
.52
44
.51
68
16
72
94
83
19
24
89
25
08
43
79
.23
10 8 5
7 07
7 99
2 06
9 70
4 52
7 89
7 50
2 50
2 0
3 7
3 9
15 3 4
3
3
5
3
4
2
5
8
15
9
7
3
3
5
3
8
13 48
9 29
12 44
12 8 8
PPT
HOUR
1 .
0.
5.
0.
94 .
22.
24.
0.
26.
28.
30.
32.
34 .
36 .
38.
40 .
44 .
46 .
48 .
50.
52.
56 .
60.
64.
68.
0.
14 .
72 .
76.
3 .
78 .
38.
80.
0.
82.
0.
84 .
0.
86.
0.
88 .
0.
90.
0.
92.
0.
94 .
0.
96.
0.
98 .
0.
0. 100.
0.
0.
0.
0.
2.
0.
0.
12 .
7 .
0.
0.
0.
2.
63 .
142.
57 .
SHORT TERM MONITORING OF DITCH WATER (NOVEMBER 14 - 16, 1983)
TIME
11/14/11'
11/14/13
11/14/15
11/14/17
11/14/19
11/14/21
11/14/23
11/15/01
11/15/03
11/15/05
11/15/07
11/15/09
11/15/11
11/15/13
11/15/15
11/15/17
11/15/19
11/15/21
11/15/23
11/16/01
11/16/03
11/16/05
11/16/07
11/16/09
11/16/1 1
PH
sc
N03
NH4
0P04
FE
TP04
MG
CA
NA
K
CR
PPT
HOU
1 .
14 .
3 .
5 .
45 .
7 .
33 .
9 .
28 .
11 .
70.
87 .
13 .
43 .
15 .
17 .
15 .
4 .
19 .
10.
2 1 .
1 1 . 23 .
25 .
0.
27 .
0.
2 .
29 .
3 1 .
0.
13 .
33 .
35 .
40.
37 .
43 .
34 .
39 .
4 1 .
32 .
43 .
50.
93 .
45.
47 .
30.
49:
2 .
0.
5
5
6
5
7
7
7
7
7
7
6
6
6
6
6
6
6
6
6
. 54
28
.22
33
03
23
21
26
15
01
88
68
67
60
49
67
49
30
31
17
10
9
15
53
55
58
65
66
64
4 1
42
14
7
9
12
6
6
6
0
8 0
3 0
0
2
2
2
2
2
2
5 2
1
3 0
4 0
0 0
4 0
4 0
2 0
4 0
31
69
18
91
52
14
26
51
51
97
81
70
32
14
22
22
16
17
22
0 07
0 02
0 06
0 05
0 03
0 04
0 01
0
0
0
0 02
0 04
0 07
0 02
0 06
0 07
0 06
0 03
0 03
0 023
0 023
0 044
0 052
0 080
0 071
0 072
0 071
0 055
0 06 1
0 058
0 059
0 065
0 050
0 04 1
0 046
0 021
0 024
0 027
0 06
0 05
0 06
0 06
0 09
0 09
0 09
0 09
0 09
0 09
0 09
0 08
0 07
0 05
0 05
0 05
0 03
0 03
0 03
0
0
0
0
0
0
0
0
0
0
0
. 05
. 43
.4 1
.41
. 37
. 42
.4 1
. 40
. 23
.04
OS
0
1
1
1
2
2
2
2
1
0
0
0
0
0
0
0
050
051
057
15
54
97
85
15
05
22
14
31
22
1 15
100
090
073
105
065
2
1
2
2
6
7
7
8
7
8
3
6
3
2
2
2
2
2
1
2
9
0
6
6
7
1
1
6
6
4
1
7
3
5
8
7
0
0
0
0
2
2
2
2
2
2
2
1
0
0
0
0
0
0 0
9 0
50
33
44
56
49
77
54
84
88
80
54
80
81
50
44
42
33
37
28
0 . 25 9
0 . 25 8
0 . 30 4
0 3 5 15
2 .00
2 50
2 30
2 60
2 60
2 50
2 25
1 45
0 35
0 20
0 20
0 20
0 20
0 25
0 15
17
2
2
3
7
15
33
3
7
2
. 7
. 2
. 3
. 8
. 2
. 9
.7
.0
.0
. 5
. 4
.6
.1
. 5
3 .0
2 .1
5 .0
135
DITCH SEDIMENT AND OVERLYING WATER DATA
WATER A N A L Y S I S
FILE
SC
NH4
PH
NO 3
2-1 1-83
WA- 1
5. 9 0 21
0 . 45 0 . 19
WA-2
5 . 65 22
0 . 44 0 . 19
W8-1
3. 87 19
0..37 0 . 19
WB-2
5. 71 17 .5
0,.50 0 . 1 1
WC-1
5. 43 22 .5
0.. 34 0 . 19
WC-2
5 .92 18
0..44 0 . 17
6-03-84
WA- 1
6. 82 61
0.. 13 0 . 79
WA-2
6. 86 64
0 .,08 0 . 76
WB-1
6. 91 37
0 .,09 0 . 02
WB-2
6. 95 36.
0 . 07 0 . 0 9
WC- 1
6. 85 31 ,
0 . 05 0 .
WC-2
6. 83 31 .
0 . 05 0 . 06
SEDIMENT A N A L Y S I S
FILE
/£FE
VoMG
'/J - P
2-11-83
SA-1
4 .058
1 .232
0 .989
,
1 . 5 4 0 4 .229
SA-2
1 . 152
1 .235
SB-1
3 .933
1 . 174
1 .217
SB-2
1 .091
3 ., 572
SC-1
1 .094
0 .. 635 3,. 459
SC-2
0., 782 3 ., 532
1 .083
6-03-84
SA-1
1.,475
3 .608
1 . 1 10
SA-2
1. 451
3 . 778
1 .051
SB- 1
3. 540
1 .095
0 . 865
SB-2
1. 0 4 6
4 . 1 19 1 . 164
SC- 1
0 . 963
3 . 208
0..964
SC-2
1. 0 9 9
4 . 180
1 ,131
,
0P04
TP04
FE
MG
1 .71
1 .53
0,.83
1 ..17
0 .52
0 .64
0 . 33
0 . 15
0., 13
0,. 34
0.
. 10
0.
.07
0.
0.
. 1 142. 2
. 143 2 . 3
.089 2. 5
. 104 2. 7
.082 3-. 2
. 0 8 9 3. 2
0.
0.
0.
0.
0.
0.
0 .. 1 19
0 ., 154
0 .,070
0 . 065
0 . 063
0 . 064
0 .,09
0 .. 1 1
0 .,06
0 . 05
0 , 04
0 . 04
.65
.45
. 1 1
.09
. 12
. 13
. 57
.64
. 200
. 198
. 147
1 . 50
2. 20
2. 38
1 .25
1 .25
1 .05
1 .06
%CA
2 .541
2 . 269
2 . 210
1 . 977
2 .050
1 , 983
2.. 299
2 .044
2 . 240
1 .453
1 ,940
1 .193
*NA
1 . 798
1 . 327
1 .315
1 . 14 1
1 .547
1 . 66 1
1 . 420
1 .047
1. 630
1. 390
0 .8 13
1 , 103
CA
6. 0
6. 0
4 . 22
4 .08
3 . 18
3. 22
%Y.
^CR
0 . 458
0 . 436
0.. 4 7 0
0 445
0 , 438
0 . 465
0 .0964
0 . 1539
0,. 1302
0,. 1 165
0 ,,0625
0. 0780
0.
0.
0.
0.
0.
0.
435
368
498
446
380
445
0.
0.
0.
0.
0.
0.
1238
3006
1115
1486
1301
1260
NA
K
41
43
39
40
40
41
CR
0.. 20 3 . 7
0.. 20 17 . 8
0 ., 15 1 1. 7
0 , 15 24 . 9
0. 20
5 .9
0,,20
5 .0
0.
0.
0.
0.
0.
0.
51
51
29
27
35
37
5,.6
5 .9
4 ., 2
5 .9
,
6 .2
4 .9
136
APPF.NT)rX F -
LABORATORY STUDY CHFMTCAL DATA
COLUMN EXPERIMENT SOIL DATA
RUN
1
Column
DEPTH
0.
15.
30.
Column
DEPTH
0.
15 .
30.
RUN 2
Column
DEPTH
0.
15.
30.
Column
DEPTH
0.
15 .
30.
Co 1umn
DEPTH
0.
15.
30.
1
%T-P
0.2835
0.2577
0.2213
2
%T-P
0.1734
0.2763
0.2308
1
%T-P
0.2305
0.2266
0.2741
2
%T-P
0.2461
0.2688
0.2128
3
%T-P
0.2284
0. 1934
0.1744
%NA
%K
2.234
0.570
0. 541
2.460
2 . 293 .0.530
%FE
4 . 173
4 . 324
4.000
%CR
0.0192
0.0094
0.0082
7.MG
1 . 306
1 . 472
1 . 431
%CA
2 . 379
2.571
2.594
%FE
3.753
4.396
4.306
%CR
0.0076
0.0145
0.0108
%MG
1". 423
1 .507
1.411
%CA
%NA
2.681
2.516
2.324
2.400
2 . 568 2.490
%FE
4.390
4.234
4 . 262
%CR
0.0358
0.0895
0.0830
%CA
%MG
1 . 426 2 . 446
1 . 443 2.596
1 . 4 8 0 2 . 546
%NA
2 . 157
2.491
2 . 183
%K
0. 598
0.577
0. 558
%FE
4.268
4 .046
3.660
%CR
0.0495
0.0750
0.0560
%MG
1 .497
1 . 358
1 . 257
%CA
2.627
2 . 533
2. 382
%NA
2. 175
2.419
2 . 527
%K
0.575
0. 586
0. 541
%MG
1 . 384
1 .472
1 . 340
%CA
°/,NA
%K
2 . 203 2 . 330 0. 571
2 . 446 2 . 327 0. 609
2 . 654 0. 609
2.486
%FE
%cn
3 . 837 0.0855
3.919
0. 1 155
3.907
0.1355
%K
0.630
0.585
0. 5 9 0
COLUMN EXPERIMENT WATER DATA
TIME
SC
NO 3
NH4
TP04
FE
MG
CA
NA
K
RUN 1 • COLUMN 1
0.
2.
4 .
6.
8 .
20.
24 .
45.
RUN 1
0.
2 .
4 .
6 .
8 .
20.
24 .
45 .
ao.
3.91
0. 59
0.. 16
. 20
0 . 56
132.
104 .
90.
58.
22.
26 .
22.
0.88
0. 77
0. 46
0. 19
0. 25
1. 8 1
2 .4 0
2 .49
2 .07
1 .32
0.. 33
0.. 70
1. 7
1 .. 7
0. 6
. 22
. 18
.07
.07
.06
6 . 7 2 . 12 0.. 77
0..68
0.. 39 3 . 3 1 .33 0.. 68
0 .09
0 . 55 0.. 30 0.. 45
0..08
0 . 48 0.. 35 0 . 40
0..07
0.. 50 0. 17 0. 30
3.84
0. 44
0. 16
. 17 0. 97
0.41
0.44
0. 44
0. 18
0.09
1 .47
1 .58
0. 95
1 .02
0. 35
0. 10
0. 30
0. 40
0. 40
0. 40
COLUMN
120.
100.
52.
40.
36 .
25 .
20.
14 .
6. 7
1 .. 55 0.. 54
2
. 10
. 10
.06
0.
. 10
0. 22
0. 20
0. 1 1
0. 10
0. 09
1 1 8.
1. 14 0. 42
3 .2
0. 82
2 .7
0. 66
0.. 94 0. 26
0. 84 0. 19
0. 81 0. 09
0. 50
0. 45
0. 34
0. 30
0. 20
137
COLUMN EXPERIMENT WATER DATA CONTINUED
TIME
RUN 2
SC
0
0.. 5
1 .0
.
1 ,. 5
2..0
2. 5
3. 0
3 .5
4 .0
4 .5
5 .0
5. 5
S. 0
8 .0
24.
45.
9.
, 79
9 .05
.
6., 17
3.. 10
2..24
1 ,, 54
1 ,, 27
0 .67
0,.55
0,.47
0 .43
0 .37
0 .32
0 . 34
0 . 12
0 .68
COLUMN
0
100.
0 . 5 98.
1 .0
75.
1 .5
56.
2..0
50.
2..5
57 .
3.,0
79.
3..5
36.
4 .0
.
86.
4,
. 5 76.
5. 0
75.
5 .5
69.
6 .0
64 .
8 .0
54 .
24
31 .
45
14 .
RUN 2
NH4
TP04
FE
MG
CA
NA
K
COLUMN 1
154 .
0
0 .5 1S0.
1 .0 103
74
1 .5
2 .0
SO.
51 ,
2 .5
48 .
3 .0
44 .
3 .5
4 .0
39.
37,
4 .5
40.
5 .0
31
5 .5
28 .5
6 .0
24
8 .0
24
22,
30
45
RUN 2
N03
85.
125.
129 .
103 .
87 .
58.
60.
65 .
61 .
47 .
38 .
37.
33. 5
29. 5
18 .
20.
0,. 13
0,. 10
0,.07
0 .06
0 . 10
0 . 16
0,.08
0 .08
0 .05
0 .06
0 .08
0 .05
0 .08
0 .08
0 .09
0 . 13
50
65
24
20
73
0 .86
0.. 78
0..78
0. 66
0. 47
0. 85
1. 76
2 .94
3 .58
4 .84
4 .30
4 .28
4 , 54
3.. 78
1 .95
.
0.,91
0 . 12
0,. 1 1
0..08
0. 12
0. 18
0. 19
0. 20
0. 80
3 .0 0
6 .20
10. 2
9 .8
9.. 4
7 .3
,
1 ,, 6
0..60
17
35
30
14
22
14.5
12.1
9.5
7 .2
5.5
4.9
4.5
4. 1
3.4
3. 1
2.9
2.7
2.6
2 . 2
1.11
0. 85
6.5
0.84
3.80 0.83
3.06
2.30 0.55
1.80 0.50
1.57 0.53
1.45 0.42
1.21 0.39
1 .06
1.00 0.35
0.93 0.34
0.85
0.74 0.30
0.56 0.25
0.23 0.10
0.11 0.12
2
4.
, 73
3.. 84
2. 89
1 .61
1 .16
0. 53
0. 41
0. 46
0. 48
0. 52
0. 45
0,.42
0.. 37
0.,35
0. 12
0.,03
COLUMN
14 . 2
12 . 1
9. 5
6. 2
5. 1
4. 2
12
3. 7
21
3 .3
2 .9
19
2 .6
2 .5
20
2. 4
2
20
14
1 .7
1. 3
10
1 .7
12
0.,87
0.. 84
0.. 72
0,.57
0 . 54
0,. 44
0,.42
0 .41
0 .39
0 .34
0 .32
0 .25
0 . 35
0 . 33
0 .09
0 .03
20
20
25
25
23
21
26
15
07
8.6
9. 1
3.73 0.76
1 . 9
7 . 3 3.23 0.75
6 .9
6 . 5 2.92 0.66
4. 8
5.0
2.15 0.52
4. 1
a. 1
1.80 0.47
3 .05
.
1 . 79 1.61
5 .8
.
6. 1 2.11 0.73
5. 5
5.6
2.08 0.84
5 .0
.
4 . 9 1 .92
4 .0
3.8
1.60 0.89
3 .8
4.0
1.80 0.84
2.5
2 .5
1.18 0.85
2 .0
2.0
1.03 0.84
1. 4
1 . 3 0.70
0 . 42 0. 34 0.2 1 0.42
0 . 42 0. 29 0.09 0.19
3
4 .68
9. 30
9. 79
5 .44
2. 37
0. 46
0. 21
0. 17
0. 19
0. 27
0. 23
0. 27
0. 29
0. 32
0. 13
0. 09
0. 33
0. 60
0. 60
0. 58
0. 54
0. 39
0. 42
0. 46
0. 50
0. 48
0. 66
0. 78
0. 84
1. 21
1. 07
1. 02
0. 12
0. 12
0. 08
0. 12
0. 16
0. 08
0. 14
0. 12
0. 12
0. 14
0. 20
0. 28
0. 16
0. 40
1. 40
0. 60
10
20
16
12
07
07
06
07
13
16
18
17
14
10
05
7. 4
10 .9
1 1. 3
8. 5
6. 1
4. 6
5..0
4,
.8
4 .4
3. 8
3 .1
2. 7
2 .5
1 .3
0. 34
0. 44
8. 7
1 1. 5
12 . 2
9 .0
7. 3
5 .5
5 .8
5. 8
5. 4
4. 5
4 .0
.
3. 3
3 .0
1 ,, 7
0. 30
0. 34
3 . 13 0 . 57
3 . 45 0..70
3 . 82 0.. 75
3 . 48 0. 62
2 .88 0.. 56
2 . 40
2 .00 0. 50
2.. 1 10. 51
1 .67 0. 49
1 .. 32 0. SO
1 .. 14
1 .
02 C. 49
0..87 0. 49
0..76 0. 46
0. 22 0. 32
0. 19 0. 27