United States
Environmental Protection
Agency
EPA-600/4 V>2 030a
May 1982
Research and Development
Environmental
Monitoring at
Love Canal
Volume I
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EPA-600/4-82-030 a
May 1982
ENVIRONMENTAL MONITORING AT LOVE CANAL
Volume I
U.S. Environment.:-.! Pictco^rj ,^-ncy
ii^on V, L;br?rv " "
•• y- South r-., Itvrn C"> ,;:[
'- ---^o, iliinuiG 60004
Office of Research and Development
U.S. Environmental Protection Agency
401 M Street, S.W.
Washington, D.C. 20460
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DISCLAIMER
This document was initiated prior to the Agency's recently
instituted peer and policy review system. However, the report
has been reviewed by many scientists within the U.S. Environ-
mental Protection Agency, and approved for publication. Mention
of trade names or commercial products does not constitute en-
dorsement or recommendation of use.
The reader is cautioned to consider this report in its en-
tirety. Reliance upon or use of any individual segment of this
report without consideration of the whole document may be mis-
leading and could possibly lead to erroneous conclusions.
For sale by the Superintendent of Documents. U.S. Government Printing Office
ton, B.C. 20402
US.
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FOREWORD
This report describes the results of a comprehensive multi-
media environmental monitoring study conducted by the U.S. En-
vironmental Protection Agency (EPA) at Love Canal, in Niagara
Falls, New York. EPA was directed to conduct this study in
response to a presidential state of emergency order that was
declared at Love Canal on May 21, 1980. The purpose of this
study, which was conducted during the summer and fall of 1980,
was to provide an environmental data base on which decisions
could be made regarding the habitability of residences in the
Love Canal emergency declaration area. Due to the existence of a
state of emergency at Love Canal, the design and field sampling
portions of the project were completed under severe time con-
straints.
The monitoring program performed by EPA at Love Canal in-
volved the collection and analysis of approximately 6,000 field
samples, making the Love Canal study the most comprehensive
multimedia monitoring effort ever conducted by EPA at a hazardous
wastes site. The precision and accuracy of the environmental
measurements obtained were documented through application of an
extensive quality assurance program. As a result, this study
exemplifies the design and execution of a state-of-the-art en-
vironmental monitoring program.
Volume I, Chapter 1, consists of an overview of the entire
project and is intended to be accessible to a wide audience. The
remainder of Volume I provides additional information concerning
the design of the project and study findings. Technical details
regarding specific aspects of the quality assurance programs used
to validate the monitoring data are included as Appendixes to
Volume I. Volumes II and III present the Love Canal monitoring
data.
The EPA environmental monitoring data have been reviewed by
the U.S. Department of Health and Human Services. The data from
the organic chemical analyses have also been reviewed by the
National Bureau of Standards (NBS). The results of these reviews
are presented in a report entitled "Interagency Review: Comments
by the U.S. Department of Health and Human Services and the
National Bureau of Standards on the U.S. Environmental Protection
111
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Agency's Love Canal Monitoring Study," available from the Nation-
al Technical Information Service. Also included in that report
is the EPA response to the NBS review.
In addition to the review performed by the National Bureau of
Standards, the EPA Love Canal report was reviewed extensively by
numerous Agency scientists. The results of these reviews have
been incorporated in this final report, and have addressed all
significant concerns expressed by the reviewers. The review
comments did not affect the major finding of the EPA multimedia
environmental monitoring study: namely, the data revealed no
clear evidence of environmental contamination in the residential
portions of the area encompassed by the emergency declaration
order that was directly attributable to the migration of sub-
stances from Love Canal.
Courtney Riordan
Acting Assistant Administrator
for Research and Development
IV
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ABSTRACT
During the summer and fall of 1980 the U.S. Environmental
Protection Agency (EPA) conducted a comprehensive multimedia
environmental monitoring program in the vicinity of the inactive
hazardous wastes landfill known as Love Canal, located in Niagara
Falls, New York. As a result of a presidential state of emer-
gency order issued on May 21, 1980, EPA was instructed to assess
the extent and degree of environmental contamination that was di-
rectly attributable to the migration of substances from Love Ca-
nal into the occupied, residential area around the former canal
defined by: Bergholtz Creek on the north? 102nd Street on the
east and 103rd Street on the southeast; Buffalo Avenue on the
south; and 93rd Street on the west. The area closest to the for-
mer canal, currently owned by the State of New York and contain-
ing the unoccupied so-called ring 1 and ring 2 houses, was ex-
cluded from the emergency declaration order.
The studies conducted at Love Canal by EPA included a major
hydrogeologic investigation, and the collection and analysis of
approximately 6,000 environmental samples consisting of water,
soil, sediment, air, and biota. An extensive quality assurance/
quality control program was applied to all phases of the analyti-
cal work to document the precision and accuracy of the monitoring
data. 'Strict chain-of-custody procedures were also employed to
assure the integrity of the monitoring data.
The EPA multimedia environmental monitoring data revealed a
limited pattern of environmental contamination in the area im-
mediately adjacent to Love Canal, probably caused by localized
and highly selective migration of toxic substances from the
former canal to the vicinity of certain ring 1 residences. The
data also revealed that contamination that had probably migrated
from Love Canal was present in those storm sewer lines that
originated near the former canal, and was present in area creeks
and rivers (primarily in the sediment) at locations near to and
downstream from the outfalls of those storm sewers.
Apart from these findings, the monitoring data revealed no
clear evidence of environmental contamination in the area encom-
passed by the emergency declaration order that was directly at-
tributable to the migration of substances from Love Canal. The
data also provided no evidence, outside of ring 1, supporting the
v
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hypothesis that swales preferentially transported contaminants
from the former canal into the surrounding neighborhood. Further-
more, the data revealed that the barrier drain system surrounding
the landfill was effectively intercepting substances migrating
laterally from Love Canal and was drawing near-surface ground
water back to the drains for collection and subsequent treatment.
In addition to the report presented in this Volume, two other
Volumes have been prepared to document the Love Canal study.
Volume II consists of a complete enumeration of all validated
field samples collected at Love Canal and Volume III consists of
a collection of statistical tabulations of the validated Love
Canal monitoring data.
vx
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CONTENTS
Page
Foreword iii
Abstract ......... ........... v
Figures . ix
Tables xii
Abbreviations and Symbols xv
Acknowledgments xviii
CHAPTER 1 Overview 1
1. 1 The EPA Monitoring Program 6
1.1.1 Selection of Sampling Sites . 6
1.1.2 Samples Collected «
1.1.3 Statistical Analysis of the Data ..... 9
1.1.4 Substances Monitored 12
1.1.5 Sampling Procedures and Sites Sampled . . 13
1.1.6 Limitations 16
1.2 Results 1«
1. 3 Conclusions 21
CHAPTER 2 Background 23
2.1 Site Location . . 23
2.2 Site History . 24
CHAPTER 3 Design of the Monitoring Studies 34
3.1 Objectives 34
3.2 Implementation 35
3.3 Quality Assurance/Quality Control (OA/QC) and
Data Validation ...... 39
3.3.1 Limits of Detection and Ouantitation . . . 43
3.3.2 Precision and Accuracy Goals 43
3.4 Data Analysis and Data Reporting ........ 45
3. 5 Limitations 47
CHAPTER 4 Results of the Investigations 49
4.1 Hydrogeologic Program ..... 49
4.1.1 Geology of the Love Canal Area 50
4.1.1.1 Geological Setting 50
4.1.1.2 Topography and Drainage 54
4.1.1.3 Occurrence of Ground Water ... 60
VII
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CONTENTS (continued)
Page
4.1.2 Geophysical Investigations , . . . 61
4.1.2.1 Objectives of the Geophysical
Investigations 61
4.1.2.2 Major Results of the Geophysical
Investigations 63
4.1.3 Hydrology of the Love Canal Area ..... 63
4.1.3.1 Ground-Water Movement ....... 66
4.1.3.2 Ground-Water Flow Modeling ... 71
4.1.4 Implications of the Hydrogeologic
Program Findings 73
4.2 Evidence of Contamination Movement 75
4.2.1 Ground-Water Contamination 77
4.2.1.1 Shallow System 77
4.2.1.2 Bedrock Aquifer .... R3
4. 2. 2 Soil Contamination 87
4.2.3 Sump Contamination 97
4.2.4 Sanitary and Storm Sewer Contamination . . 107
4.2.5 Surface Water and Stream Sediment
Contamination 116
4.2.6 Air Contamination 123
4.3 Evidence of Other Environmental Contamination . . 144
4.3.1 Drinking Water Contamination 144
4.3.2 Food Contamination 147
4.3.3 Radioactive Contamination ........ 149
4.3.4 Biological Monitoring of Contaminants . . 152
4.3.5 Dioxin ( 2, 3, 7, 8-TCDD) 156
CHAPTER 5 Summary and Conclusions 162
Appendix A Lists of Substances Monitored at Love Canal . 166
Appendix B Comparative Data and Existing Standards for
Substances Monitored at Love Canal 171
Appendix C Quality Assurance for Water Samples 221
Appendix D Quality Assurance for Soil, Sediment,
and Biota Samples 245
Appendix E Quality Assurance for Air Samples 266
Appendix F Report on the Audit of Gas Chromatography/
Mass Spectrometry Data Provided by Love
Canal Project Analytical Laboratories .... 287
Vlll
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FIGURES
Number
1 General Site Location Map 2
2 The General Love Canal Study Area ..... 3
3 Detail of the General Love Canal Study Area 4
4 Sampling Areas ......... 10
5 Love Canal Remedial Action Project Plan View 30
6 Remedial Project: Transverse View . . 31
7 Sample Page of the Data Listing Presented in
Volume II ....................... 46
8 Well A (Overburden) Installation Site Codes 51
9 Well B (Bedrock) Installation Site Codes 52
10 Generalized Columnar Section of Geologic Units
in Love Canal Area 55
11 Index Map Showing Location of Project Area and
Physiographic Provinces .... 56
12 Location of Storm Sewers Near Love Canal 59
13 Three Dimensional Plot of Shallow Electromagnetic
Conductivity Data from Canal Area 64
14 Site Map Showing Major Results of Geophysical Survey , 65
15 Completed Shallow (Overburden) Well ......... 67
16 Completed Bedrock Well 68
17 Regional Lockport Dolomite Potentiometric Surface ... 69
18 Lockport Dolomite Potentiometric Surface ....... 70
19 Overburden Static Water Table ............. 72
20 Well A Sampling Sites, Benzene, Maximum
Concentrations BO
21 Well A Sampling Sites, Toluene, Maximum
Concentrations SI
22 Well A Sampling Sites, Y-BHC, Maximum Concentrations . 82
23 Well B Sampling Sites, Benzene, Maximum
Concentrations .......... 84
24 Well B Sampling Sites, Toluene, Maximum
Concentrations . . . 85
25 Well B Sampling Sites, Y-BHC, Maximum Concentrations . 86
26 Soil Sampling Site Codes ............... 88
27 Typical Soil Sampling Configuration Used at Each Site . 90
28 Soil Sampling Sites (First), Benzene, Maximum
Concentrations ......... 93
29 Soil Sampling Sites (Second), Benzene, Maximum
Concentrations 94
30 Soil Sampling Sites, Y-BHC, Maximum Concentrations . . 95
31 Soil Sampling Sites, Cadmium, Maximum Concentrations . 96
IX
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FIGURES (continued)
Number Page
32 Sump Water Sampling Site Codes 99
33 Sump Water Sampling Sites, Benzene, Maximum
Concentrations 104
34 Sump Water Sampling Sites, Toluene, Maximum
Concentrations 105
35 Sump Water Sampling Sites, Y-BHC, Maximum
Concentrations 106
36 Storm Sewer Sampling Site Codes 109
37 Storm Sewer Sediment Sampling Sites, Benzene,
Maximum Concentrations Ill
38 Storm Sewer Water Sampling Sites, Toluene,
Maximum Concentrations 112
39 Storm Sewer Sediment Sampling Sites, Toluene,
Maximum Concentrations 113
40 Storm Sewer Water Sampling Sites, Y-BHC, Maximum
Concentrations 114
41 Storm Sewer Sediment Sampling Sites, Y-BHC,
Maximum Concentrations 115
42 Surface Water and Stream Sediment Sampling
Site Codes 117
43 Stream Sediment Sampling Sites, Benzene, Maximum
Concentrations 118
44 Surface Water Sampling Sites, Toluene,
Maximum Concentrations 119
45 Stream Sediment Sampling Sites, Toluene,
Maximum Concentrations 120
46 Surface Water Sampling Sites, Y-BHC, Maximum
Concentrations 121
47 Stream Sediment Sampling Sites, Y-BHC, Maximum
Concentrations 122
48 Air Sampling Site Codes 125
49 Outside Air Sampling Sites, Benzene, Maximum
Concentrations 130
50 Living Area Air Sampling Sites, Benzene, Maximum
Concentrations 131
51 Basement Air Sampling Sites, Benzene, Maximum
Concentrations 132
52 Concentration of Benzene in Living Area Air Samples
Collected in Canal Area Residences 135
53 Concentration of Benzene in Living Area Air Samples
Collected in Control Area Residences 136
54 Median Concentration of Benzene in Living Area Air
Monitoring Sites Located in the Declaration
and Canal Areas 137
55 Median Concentration of Toluene in Living Area Air
Monitoring Sites Located in the Declaration
and Canal Areas 138
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FIGURES (continued)
Number Page
56 Median Concentration of 1,1,2, 2-Tetrachloroethylene in
Living Area Air Monitoring Sites Located
in the Declaration and Canal Areas 139
57 Median Concentration of Benzene Observed in Air for
Each Sampling Campaign 141
58 Median Concentration of Toluene Observed in
Air for Each Sampling Campaign 142
59 Median Concentration of 1,1,2,2-Tetrachloroethylene
Observed in Air for Each Sampling Campaign 143
60 Drinking Water Sampling Site Codes 145
61 Drinking Water Sampling Sites, Chloroform,
Maximum Concentrations .. ......... 148
62 Oatmeal and Potatoes Sampling Site Codes ....... 150
63 Biota Sampling Site Codes 154
64 Sampling Site Codes for Dioxin {2,3,7,R-TCDD) 157
XI
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TABLES
Number Page
1 Summary of Love Canal Field Samples R
2 A Summary of Love Canal Sites Sampled and Represented
in the Validated Data Base 14
3 Chemicals Disposed at Love Canal by Hooker
Electrochemical Company (1942-1953) 25
4 Identification of EPA Laboratories
and Project Subcontractors 36
5 Geophysical Methods and Applications 62
6 Frequency of Detection of Contaminants in Validated
Love Canal Samples 76
7 Significant Differences Observed in Extent of Shallow
System Ground-Water Contamination at Love Canal .... 79
8 Significant Differences Observed in Extent of Soil
Contamination at Love Canal 91
9 Significant Differences Observed in the Extent of
Sump Water Contamination at Love Canal 100
10 Significant Differences Observed in the Extent of
Air Contamination at Love Canal 128
11 Three Highest Concentrations of Selected Compounds
Observed in Regular Air Monitoring 133
12 Frequency of Detection of Contaminants in
Additional Validated Love Canal Samples 146
13 Minimum Detection Levels for Particular
Gamma-Emitting Radionuclides 151
14 Scope of the Biological Monitoring Program 153
15 Results of Storm Sewer Sediment Determinations for
2, 3, 7, 8-TCDD 159
A-l Substances Monitored in Love Canal
Water/Soil/Sediment/Biota Samples 166
A-2 Substances Monitored in Love Canal Air Samples .... 169
B-l Control Sites 172
B-2 U.S. Average Data 176
B-3 Air 177
B-4 Surface Water 178
B-5 Drinking Water 179
B-6 Biota 180
B-7 List of Compounds Found in Ambient Air Using
TENAX 182
xix
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TABLES (continued)
Number Page
B-8 Average Daily Concentrations of Toxic Chemicals
Found toy Singh 197
B-9 Summary of Current Standards for Substances
Monitored in Love Canal Air Samples .......... 198
B-10 Analytical Results of Chloroform, Bromoform,
Bromodichloromethane, and Dibromochloromethane,
and Total Trihalomethanes in Water Supplies
from NORS and NOMS 201
B-ll EPA National Drinking Water Regulations 202
C-l Measured Method Detection Limits in
Micrograms per Liter from Analyses of
Laboratory Control Standards 229
C-2 Estimated Method Detection Limits for
all Laboratories .......... 230
C-3 Measured Method Detection Limits in Micrograms
per Liter for Method 608 in Reagent Water 231
C-4 Percentages of Acceptable Performance
Evaluation Results 233
C-5 Summary Statistics and Lower Control Limits
for Methods 624 and 625 Surrogates from
EMSL-Cincinnati Measurements ..... 238
C-6 Relative Standard Deviations (RSD) for Organic
Analytes in Laboratory Control Standards . 242
C-7 Relative Standard Deviations (RSD) for Inorganic
Analytes in Water Samples 243
D-l Summary Statistics and Acceptance Limits for
Modified Method 624 and Modified Method 625
Surrogates from all Laboratory Measurements . 258
D-2 Relative Standard Deviations (RSD) for Organic
Analytes in Laboratory Control Standards
NBS Sediment 262
D-3 Relative Standard Deviations (RSD) for Metals
Analytes in Laboratory Control Standards
NBS Sediment 263
D-4 Mean Percent Recoveries and Standard Deviations
of NBS Certified Values in SRM River
Sediment 1645 ....... 264
E-l Volatile Organics on TENAX 271
E-2 Pesticides on Foam Plugs 272
E-3 Detection Limits for Inorganics 273
E-4 Results from Analyses of Blank TENAX Samples 273
E-5 Results from Air TENAX Duplicate Samples 27«
E-6 Results of Audits of Sampler Flow Rates 279
E-7 Results from the Analyses of Calibration Check
Samples 279
E-8 Results from the Analyses of Calibration Check
Samples by Level and Analytical System . 281
Xlll
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TABLES (continued)
Number Page
E-9 Approximate Concentrations of Calibration
Check Samples 282
E-10 Summary of Results for Polyurethane Foam
Check Samples 282
E-ll Results from the Analysis of Blind Audit
Samples by ICAP 283
E-12 Results from the Analysis of National Bureau of
Standards Standard Reference Materials by NAA 283
F-l Summary of EMSL-Cincinnati Audit of Love
Canal GC/MS Water Samples 289
F-2 Summary of the EMSL-Las Vegas and ERL-Athens
Audit of Love Canal Soil and Sediment Samples 290
F-3 Summary of the Love Canal Water Data Audit 292
F-4 Summary of the Love Canal Soil and Sediment Audit . . . 292
F-5 Summary of Non-Target Compound Audit 296
xiv
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ABBREVIATIONS AND SYMBOLS
ACEE
ACGIH
AES
amu
B
BCL
(BCL2, BCL3)
BHC
CFR
cm/s
CMTL
DEC
DOH
DOT
EMSL-Cin
EMSL-LV
EMSL-RTP
EPA
ERGO
ERL-Ada
ERL-Athens
ERL-Corvalis
ERL-Duluth
eV
9
GCA
GC/ECD
GC/FID
GC/MS
GSRI
(GSLA, GSNO)
HERL-RTP
Acurex Corporation, Energy and Environment Division
American Conference of Governmental Industrial Hy-
gienists
Advanced Environmental Systems, Inc.
atomic mass unit
Below limit of detection
Battelle Columbus Laboratories
Hexachlorocyclohexane (benzenehexachloride)
Code of Federal Regulations
centimeters per second
Compuehein/Mead Technology Laboratories
New York State Department of Environmental Conser-
vation
New York State Department of Health
New York State Department of Transporation
U.S. EPA Environmental Monitoring and Support
Laboratory, Cincinnati, Ohio
U.S. EPA Environmental Monitoring Systems Labora-
tory, Las Vegas, Nevada
U.S. EPA Environmental Monitoring Systems Labora-
tory, Research Triangle Park, North Carolina
United States Environmental Protection Agency
Energy Resources Company, Inc.
U.S. EPA Robert S. Kerr Environmental Research
Laboratory, Ada, Oklahoma
U.S. EPA Environmental Research Laboratory, Athens,
Georgia
U.S. EPA Environmental Research Laboratory, Cor-
valis, Oregon
U.S. EPA Environmental Research Laboratory, Duluth,
Minnesota
Electron volt
gram
GCA Corporation
Gas chromatography/electron capture detector
Gas chromatography/flame ionization detector
Gas chromatography/mass spectrometry
Gulf South Research Institute
U.S. EPA Health Effects Research Laboratory,
Research Triangle Park, North Carolina
xv
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ABBREVIATIONS AND SYMBOLS (continued)
HIVOL
Hooker
HRGC/HRMS
I CAP
IIT
K
kg
f
LCARA
LCS
LD
LOD
LOQ
m
Mg/kg
lag/'
mg/kg
mg/l 3
mg/m
MWRI
MS
NA
NAA
NAI
NASN
NBS
NF
ng
ng/kg
ng/t
ng/m
nm
NIOSH
N'OMS
NORS
NPDES
NTIS
NUSN
NYS
OMSQA
OSHA
PAI
PCB
pCi
High-volume sampler
Hooker Chemicals and Plastics Corporation
High resolution gas chromatography/high resolution
mass spectrometry
Inductively coupled argon plasma (emission spec-
trometer)
IIT Research Institute
hydraulic conductivity
kilogram
liter
Love Canal Area Revitalization Agency
Laboratory control standard
Less than limit of detection
Limit of detection
Limit of quantitation
meter
micrograms per kilogram
micrograms per liter
micrograms per cubic meter
milligrams per kilogram
milligrams per liter
milligrams per cubic meter
Midwest Research Institute
Mass spectrometer
Not analyzed
Neutron Activation Analysis
Negative agreement index
National Air Surveillance Network
National Bureau of Standards
Not found
nanograms
nanograms per kilogram
nanograms per liter
nanograms per cubic meter
nanometer
National Institute of Occupational Safety and
Health
National Organics Monitoring Survey
National Organics Reconnaissance Survey of
Halogenated Organics
National Pollutant Discharge Elimination System
National Technical Information Service
National Urban Soil Network
State of New York
U.S. EPA Office of Monitoring Systems and Quality
Assurance
U.S. Occupational Safety and Health Administration
Positive agreement index
Polychlorinated biphenyl
picocuries
xvi
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PE
PEDC
PFOAM
PJBL
ppb
ppm
ppt
QA/QC
QAB
RSD
SD
SDWA
SRM
SWRI
T
TCDD
TENAX
THM
TLV
TOG
TOX
TRW
TWA
WSU
ABBREVIATIONS AND SYMBOLS (continued)
Performance evaluations
PEDCo Environmental, Inc.
Polyurethane foam
PJB/Jacobs Engineering Group, Inc.
parts per billion
parts per million
parts per trillion
Quality assurance/quality control
Quality Assurance Branch, EMSL-Cin
Relative standard -deviation
Standard deviation
Safe Drinking Water Act
Standard Reference Material
Southwest Research Institute
trace
Tetrachlorodibenzo-p-dioxin
TENAX sorbent
Trihalomethanes
Threshold limit value
Total organic carbon
Total organic halogens
TRW, Inc.
Time-weighted average
Wright State University
xvn
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ACKNOWLEDGMENTS
The writing of this report was accomplished through the ex-
ceptional efforts of John Deegan, Jr. As Project Coordinator, he
provided the leadership that was essential to develop a coherent
and understandable record of what was done at Love Canal, to
determine the significance of the monitoring results, and to
produce this report. As On-Scene Coordinator, he capably and
articulately represented the Agency during a period of extreme
stress, and was responsive to the concerns of local residents.
In a project of this magnitude it is impossible to acknowl-
edge the individual contributions of the numerous other partic-
ipants without inadvertently omitting someone. Therefore, a
general acknowledgment of the immense commitment of time and
energy contributed by the hundreds of EPA and contractor person-
nel involved in the conduct of this study must suffice, including
members of: the U.S. EPA Environmental Monitoring and Support
Laboratory, Cincinnati, Ohio (EMSL-Cin), Robert L. Booth, Acting
Director; the U.S. EPA Environmental Monitoring Systems Labora-
tory, Las Vegas, Nevada (EMSL-LV), Glenn E. Schweitzer, Director;
the U.S. EPA Environmental Monitoring Systems Laboratory,
Research Triangle Park, North Carolina (EMSL-RTP), Thomas R.
Hauser, Director; the U.S. EPA Robert S. Kerr Environmental Re-
search Laboratory, Ada, Oklahoma (ERL-Ada), Clinton W. Hall,
Director; and the GCA Corporation, Leonard M. Seale, General
Manager, Technology Division, and subcontractors. The dedication
of these people to the task was essential for the study1 s com-
pletion.
Because of the important contributions certain individuals
made to this project their efforts deserve to be identified. To
begin with, the overall management of this project was the re-
sponsibility of Courtney Riordan, Director of the Office of Moni-
toring Systems and Quality Assurance (OMSQA). Without his con-
tinued oversight and guidance, this project would not have been
completed satisfactorily. The Project Director for the field
monitoring portion of the project was Thomas R. Hauser, EMSL-RTP;
Steven M. Bromberg, EMSL-RTP was the Project Officer.
xvin
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The following individuals also made major contributions to
the project: William L. Budde (QA Officer for water analyses,
Appendixes C and F) and John A. Winter (QA water samples) EMSL-
Cin; Steven K. Seilkop (statistical analysis and consulting),
EMSL-RTPj Jack W. Keeley, D. Craig Shew, and Jerry T. Thornhill,
ERL-Ada and Paul Beam, Office of Water and Waste Management
(hydrogeologic program); Gerald G. Akland and Terrence Fitz-
Simons (statistical consulting), Thomas A. Hartlage (air sam-
pling), Thomas C. Lawless (data management), and John C. Puzak
(QA Officer for air analysis, Appendix E), EMSL-RTP; Stuart C.
Black (QA Officer for soil/sediment/biota analyses), Kenneth W.
Brown (water/soil/sediment/biota sampling), Eugene P. Meier, John
A. Santolucito, Andrew D. Sauter, and Allan E. Smith (radiation
program), EMSL-LV; W. Lamar Miller and R. Charles Morgan, Office
of Solid Waste and Emergency Response! James D. Bunting and
William J. Walsh, Office of Legal and Enforcement Counsel; Thomas
G. McLaughlin, Robert B. Medz, and Frode Ulvedal, Office of
Research and Development; Robert L. Harless (dioxin analyses) and
Robert G. Lewis, HERL-RTP; James R. Marshall, EPA Region II; John
Warren (statistical consulting), Office of Policy and Resource
Management; Robert M. Bradway, David R. Cogley, Rose Mary
Ellersick, and Kenneth T, McGregor, GCA Corporation; C. Stephen
Kim, New York State Department of Health (NYS DOH); and Joseph L.
Slack, New York State Department of Environmental Conservation
(NYS DEC).
In many ways, the success of the entire program was dependent
on those individuals at the EPA Love Canal Field Office who
assisted during the monitoring portion of the project. The able
staff at the EPA Love Canal Field Office included: Christine H.
White, Helen E. Burnett, Michael A. Cinquino, and Sharon J.
Thompson.
Above all others, however, the involvement of the concerned
residents of Love Canal throughout the course of this project
must be acknowledged. Without their support, suggestions, and
cooperation this study could never have even been initiated, let
alone completed.
xix
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CHAPTER 1
OVERVIEW
On May 21, 1980 President Carter issued an order declaring
that a state of emergency existed in the area of Niagara Falls,
New York known as love Canal (Figure 1). This order was issued
out of concern that toxic chemical wastes, which had been buried
in a once partially excavated and now filled canal, were con-
taminating the adjacent residential areas and were subjecting
residents to increased health risks. As a result of this order,
the United States Environmental Protection Agency (EPA) was
directed to design and conduct a comprehensive environmental
monitoring program at Love Canal that would: (1) determine the
current extent and degree of chemical contamination in the area
defined by the emergency declaration order (Figure 2); (2) assess
the short-term and long-terra implications of ground-water con-
tamination in the general vicinity of Love Canal? and (3) provide
an assessment of the relative environmental quality of the Love
Canal emergency declaration area.
The emergency declaration order of May 21, 1980 affected ap-
proximately 800 families residing in the horseshoe shaped area in
Figure 2 labeled "DECLARATION AREA." In Figure 3, the outer
boundary of the Declaration Area is defined by Bergholtz Creek on
the north, 102nd Street and 103rd Street on the east and south-
east (respectively), Buffalo Avenue on the south, and 93rd Street
on the west. It should be noted that the emergency declaration
order of May 21, 1980 excluded the area in Figure 2 labeled
"CANAL AREA."
In this report, the Canal Area is the area bordered on the
north by Colvin Boulevard, 100th Street on the east, Frontier
Avenue on the south, and (approximately) 97th Street on the west.
The Canal Area contains the residences located on both sides of
97th and 99th Streets. In 1978 the State of New York (NYS) ac-
quired all but 2 of the 238 houses in the Canal Area (including a
few houses on the north side of Colvin Boulevard), restricted
virtually the entire Canal Area from public access by means of a
guarded 8-foot high cyclone fence, and closed the public elemen-
tary school on 99th Street. The houses in the Canal Area consist
of the so-called "ring 1" and "ring 2" houses. Those 99 houses
whose backyards adjoin the inactive landfill have been referred
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Figure 1. General Site Location Map.
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DECLARATION AREA —
Figure 2. The General Love Canal Study Area,
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th STREET
DB- 99th STREET
DEURO DR.
Figure 3. Detail of the General Love Canal Study Area.
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to as ring 1 houses, while the houses on the east side of 99th
Street, on the west side of 97th Street, and immediately opposite
the landfill on the north side of Colvin Boulevard were referred
to as ring 2 houses. (See Figure 2). The former canal was lo-
cated in the area encircled by the ring 1 houses and at one time
was approximately 3,000 feet long, 80 feet wide, and has been
estimated to have been from 15 to 30 feet deep.
The 800 families residing in the Declaration Area lived
within approximately 1,500 feet of the former dump site. Of these
800 families, approximately 550 lived in single-family dwellings
(located mainly to the north and east of the Canal Area), 200
lived in a multiple-family complex of apartment buildings known
as the La Salle Development (located to the west of the Canal
Area), and 50 lived in a cluster of senior citizen garden apart-
ments (also located to the west of the Canal Area). As part of
the emergency declaration order, all persons residing in the Dec-
laration Area were eligible for temporary relocation, at U.S.
government expense, for a period of up to 1 year while environ-
mental monitoring was conducted. Approximately 300 families (or
an eligible member of a family) took part in the temporary relo-
cation program. The temporary relocation program was managed and
funded by the Federal Emergency Management Agency.
On October 1, 1980 President Carter and Governor Carey of
New York signed an agreement providing $20 million for the volun-
tary permanent relocation of all residents living in the Love
Canal Declaration Area. An agency of the State of New York, the
Love Canal Area Revitalization Agency (LCARA), was established to
manage the permanent relocation program and to plan for future
use of the acquired properties. As of May 1, 1982 LCARA records
revealed that approximately 570 families had been permanently
relocated out of the Love Canal Declaration Area.
The EPA Love Canal final report consists of this Volume and
two companion Volumes. This Volume contains a description of the
design of the monitoring studies, the results of the investiga-
tions, a summary of the major findings, and conclusions and rec-
ommendations. Volume II consists of a complete listing of the
analytical results obtained from all validated field samples col-
lected at Love Canal. Volume III contains a set of statistical
tabulations that summarize the Love Canal monitoring data accord-
ing to various geographical areas of interests, and thus charac-
terizes the extent and degree of environmental contamination in
the Love Canal Declaration Area. Other documentation is also
available that describes in detail certain aspects of the EPA
Love Canal monitoring program which are only briefly reported
here. This documentation has been prepared under contract, and is
available to the public through the National Technical Informa-
tion Service (NTIS). The material consists of: (!) an extensive
four volume set of sampling and analytical protocols and quality
assurance procedures entitled Quality Assurance Plan, Love Canal
Study, LC-1-619-026, by GCA Corporation; (2) a report entitled
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Love Canal Monitoring Program, GCA QA/QC Summary Report, by GCA
Corporation; (3) a report entitled Geophysical Investigation Re-
sults, Love Canal, New York,, by Technos, Inc.? (4) a report en-
titled TheGround-Water Monitoring Program at Love Canal, by JRB
Associates? and (5) a report entitled Final Report on Ground Wa-
ter FlowModeling Study of the Love Canal Area, New York, by Geo-
trans, Inc.
1.1 THE EPA MONITORING PROGRAM
The EPA multimedia environmental monitoring program at Love
Canal was designed and conducted under the direction of the Of-
fice of Research and Development, through its Office of Monitor-
ing Systems and Quality Assurance (OMSQA). Contract costs for
the project were $5,4 million. GCA Corporation of Bedford, Mas-
sachusetts was the prime management contractor. A total of 18
subcontractors were involved in sample collection and analytical
laboratory work.
Field sampling activities were started at Love Canal on Au-
gust 8, 1980 and were concluded on October 31, 1980. During that
time period, more than 6,000 field samples were collected and
subsequently analyzed for a large number of substances known (or
suspected) to have been deposited in the inactive hazardous
wastes landfill. The analyses performed on the samples collected
at Love Canal resulted in the compilation of approximately
150,000 individual measurements of environmental contamination
levels in the general Love Canal area. A comprehensive quality
assurance/ quality control (QA/QC) program, involving the anal-
ysis of 5,743 QA/QC samples, was applied to all phases of the
analytical work performed during the project to document the
precision and accuracy of the analytical results. Detailed re-
ports describing the QA/QC programs are included as Appendixes C
through E of this Volume. The integrity of the data was assured
through the use of strict chain-of-custody procedures that fully
documented the collection, transportation, analysis, and report-
ing of each Love Canal sample.
1.1.1 Selection of Sampling Sites
The selection of sampling locations was designed to accom-
plish three objectives: first, to monitor the Declaration Area
using a statistically valid sampling design so that estimates of
characteristic environmental concentrations of contaminants could
be obtained| second, to locate and trace pathways of chemicals
that had migrated from the former canal? and third, to obtain
multimedia environmental measurements for the purpose of validat-
ing the presence of suspected transport pathways. In order to
achieve these objectives, the following guidelines were used for
site selection purposes.
1. Written permission of the property owner/occupant had to
be obtained prior to initiating sampling activities at
any site.
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2. Simple random sampling of sites was to be employed to
obtain representative coverage of the entire Love Canal
Declaration Area.
3. Suspected transport pathways (based on information ob-
tained from prior investigations conducted at Love Ca-
nal) were to be sampled as close to the former canal as
was possible, and followed away from the former canal as
far as was feasible. This sampling was performed in
order to ascertain if contamination in the Declaration
Area was directly attributable to Love Canal.
Pathways sampled included:
a- swales—former low-lying soil features in the vicin-
ity of Love Canal that surface-water runoff once
preferentially followed. The locations of known
former swales in the general Love Canal area are
identified in Figure 2.
D- wet areas—residential areas where standing surface
water once tended to accumulate (the NYS wet/dry
designation was used for classification purposes).
c. sand lenses—sandy deposits in soils through which
ground water could readily move.
<3. buried atiIities — storm and sanitary sewers that
were located in close proximity to the canal.
e- other pathways—information obtained from local
residents directed sampling activities to numerous
areas of suspected chemical migration.
4. Creeks and rivers in the general vicinity of Love Canal
(particularly near storm sewer outfalls in Black Creek
and the Niagara River) were to be sampled to determine
the extent and degree of contamination in those waters
resulting from the discharge of contaminated water and
sediment from storm sewer lines, or from other (unknown)
sources.
5. Multimedia measurements were to be conducted at selected
sampling sites.
6. Control sampling sites were to be selected such that
they were physically similar to Declaration Area sites,
except that they were to be sufficiently distant from
the former canal so as to be free from potential contam-
ination related directly to Love Canal, and not be loca-
ted near any other known hazardous waste landfill areas.
Control sites were selected throughout the greater
Niagara Falls area, and on Grand Island (located south
of Niagara Falls). See Table B-l in Appendix B for more
detailed information on the location of control sites.
7
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7.
Indoor air monitoring was to be performed only in unoc-
cupied residences in order to reduce the potentially
confounding influence of airborne contaminants that
might be present due to habitation activities.
1.1.2 Samples Collected
A total of 6,853 field samples were collected by EPA during
the Love Canal monitoring program. Of these samples 6,193 were
analyzed and 5,708 were validated through application of an ex-
tensive QA/QC program, which involved the analysis of an addi-
tional 5,743 QA/QC samples. In total, the validated Love Canal
data base contains the results from analyses performed on 11,451
samples (field samples plus QA/QC samples). Table 1 reports the
number of field samples collected, analyzed, and validated ac-
cording to each environmental medium sampled.
TABLE 1. SUMMARY OF LOVE CANAL FIELD SAMPLES
Medium
Water
Soil
Sediment
Air
Biota
Totals
Samples
Col-
lected
2,687
1,315
290
2,089
472
6,853
Samples
Ana-
lyzed
2,457
1,156
266
2,024
293
6,193
Samples
Vali-
dated
2,065
1,132
259
1,967
285
5,708
Percent
Rejected
by QA/QC
14.6
0.7
2.4
2.6
1.5
6.8
Percent
Other*
8.5
13.2
8.3
3.2
38.1
9.9
Percent
Vali-
dated
76.9
86.1
89.3
94.2
60.4
83.3
"I" Includes samples that were damaged, lost, not resported, etc.
Note: Percentages are based on the number of samples collected.
The Declaration Area was subdivided into 10 sampling areas
that facilitated the use of statistical estimates of typical
environmental concentration levels of substances monitored
throughout various sections of the general Love Canal area.
Sampling areas were defined (as feasible) according to those
natural and manmade physical features of the Declaration Area
that might be related to chemical migration pathways. Conse-
quently, the likelihood was increased of more readily permitting
the potential identification of chemical concentration gradients
of substances that had migrated from the former canal. Typical
physical boundaries of the sampling areas included: (1) streets,
whose buried utilities (such as storm sewer lines) might serve as
barriers to, or interceptors of, the subsurface migration of
chemicals, and whose curb drains would serve as barriers to
or collectors of overland flow; and (2) creeks, which serve as
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natural recharge/discharge boundaries to the shallow ground-water
system in the area. Within each of the 10 sampling areas, sites
were both intentionally selected to maximize the probability of
detecting transport pathways (for example, purposely locating
sampling sites in former swales, sand lenses, and wet areas), and
randomly selected to provide a statistically representative
sample of residences. The fenced Canal Area compound was also
sampled, and was identified as sampling area 11. Figure 4
depicts graphically the boundaries of sampling areas 1 through
11.
In addition to the 11 geographical sampling areas just de-
scribed, a number of other sites outside the Declaration Area
were sampled and, for convenience, have been grouped according to
sampling area designations (even though they do not necessarily
refer to physically contiguous geographical areas). For example,
sampling area 97 consisted of those sites located outside the
boundary of the Declaration Area that were sampled at the expli-
cit request of area residents. Sampling area 97 sites were not
considered control sites. Another sampling area, referred to as
98, consisted of sites (including one site in the Declaration
Area) that were intentionally selected for a special ambient-air
monitoring study to determine transport patterns and background
levels of airborne pollutants. Finally, sampling area 99 con-
sisted of those sites explicitly selected as control sites for
each environmental medium sampled, and those sites that were ex-
plicitly selected as control sites for comprehensive multimedia
sampling. Due to the distance of sampling area 99 sites from the
Declaration and Canal Areas, they are often not displayed in sub-
sequent figures identifying medium-specific sampling locations.
Both the number of sites sampled and the number of samples
collected in each sampling area varied according to the environ-
mental medium sampled. Air was the only medium for which there
was an explicit attempt to sample an equal number of sites in
each sampling area. For all other media, the intensity of sam-
pling in a sampling area was a function of distance from the
former canal (that is, sampling intensity decreased with dis-
tance), availability of the medium for sampling purposes (for
example, the sampling of sump water was contingent on the pre-
sence of a sump in a residence), and the appropriateness of the
sampling area approach for the medium sampled. As an illustra-
tion of this last point, note that the sampling area approach to
characterizing bedrock ground-water quality was rejected as in-
appropriate because bedrock ground-water movement was recognized
as obviously not constrained by street boundaries.
1.1.3 Statistical Analysis of the Data
In order to perform statistical analyses on the monitoring
data, the data were aggregated (by medium and sample source) ac-
cording to Declaration Area (sampling areas 1 through 10), Con-
trol Area (sampling area 99), and Canal Area (sampling area 11).
-------
NOTE: THi DECLARATION AREA CONSISTS OF SAMPLING AREAS 1 THROUGH
Figure 4. Sampling Areas,
10
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The statistical tabulations and analyses performed on the aggre-
gated monitoring data (presented in Volume III) consisted of sub-
stance-by-substance comparisons of frequencies of detections and
median concentration levels observed in each of the three data
aggregating units (that is, Declaration, Control, and Canal
Areas).
The extent of environmental contamination in an area of in-
terest (for example, the Declaration Area) was defined as the
percentage of times a substance was identified as present at a
"trace" or greater concentration level in the field samples ana-
lyzed and validated. A difference of percentages test, using
Fisher's exact test to compute probability values, was used to
determine if statistically significant differences in the extent
of chemical contamination existed between the three aggregating
units. (See, for example, Y. M. M. Bishop, S. E. Fienberg, and
P. W. Holland, Discrete MultivariateAnalysis, M. I. T. Press,
1975, 364). The degree of environmental contamination in an area
of interest was defined as the median concentration of all field
sample measurements for a substance in the aggregating unit of
interest. A difference of medians test, using Fisher's exact test
to compute probability values, was used to determine if statisti-
cally significant differences in the degree of chemical contami-
nation levels existed between the Declaration, Control, and Canal
Areas. (See, for example, A. M. Mood, F. A. Graybill, and D. C.
B°es, ^ntrg d u c tion _to the_JTheo£y__of_Stat.i s t i c s, McGraw-Hill,
1974, 521).
Other statistical procedures used to sumrnariEe the vast
amount of data collected at Love Canal by EPA and presented in
Volume III consisted of grouping the data into frequency distri-
butions, with intervals defined according to the concentration
levels observed; computing various percentiles of interest; re-
porting finite (quantified) minimum and maximum observed concen-
trations; and computing the mean (arithmetic average) value of
the observed finite concentrations.
The statistical criteria used to aid in a determination of
the presence of Love Canal-related environmental contamination in
the Declaration Area were designed to achieve three objectives:
(1) test the validity of the postulated process of contaminant
movement from the former canal into the Canal Area, and from the
Canal Area into the Declaration Area; (2) safeguard the public
health by establishing a requirement of using only lenient sta-
tistical evidence (that provides a margin of safety) to assess
the extent and degree of contamination in the Declaration Area;
and (3) obtain acceptably high power in the statistical tests
employed that might otherwise have been affected adversely (in
certain instances) by the relatively small number of control
sites samples that could be collected during the short sampling
time period available for conducting this study.
11
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1.1.4 Substances Monitored
Due to time and budgetary constraints, the EPA monitoring
program at Love Canal was intentionally directed at the identifi-
cation of a finite number of chemicals in each sample collected.
In order to increase the efficacy of this approach, efforts were
devoted to developing lists of targeted substances that would be
routinely monitored in each specific sample type collected at
Love Canal. To this end, the following activities were con-
ducted: (1) samples of air and leachate were collected by EPA
directly at the former canal prior to the initiation of field
sampling activities and were analyzed comprehensively; (2) the
results from previous environmental monitoring studies conducted
at Love Canal by the State of New York and EPA were reviewed; and
(3) records submitted by the former owner of the site, Hooker
Chemical and Plastics Corporation (concerning the 21,800 tons of
chemical wastes buried in the landfill) were examined. These
efforts permitted EPA to identify those substances that were most
abundant in the source, prevalent in the environment, and of
toxicological significance. The end result was the construction
of 2 lists of targeted substances; a list of approximately 150
substances for water/soil/sediment/biota samples; and a list of
50 substances for air samples. The specific substances monitored
at Love Canal are listed in Tables A-l and A-2 in Appendix A of
this Volume.
The EPA monitoring program conducted at Love Canal represents
a directed, comprehensive effort in environmental monitoring at a
hazardous wastes site. Due to the large number of environmental
samples analyzed and the large number of targeted substances mon-
itored, it is unlikely that significant amounts of contaminants
that had migrated from Love Canal would have been undetected.
Furthermore, the intentional inclusion of specific substances on
the target list that were known to be present in Love Canal, and
which (due to their physical and chemical properties) might also
serve as effective and efficient indicators of subsurface migra-
tion of leachate, was designed to permit a determination and as-
sessment of chemical migration from the source.
The EPA monitoring program at Love Canal also included the
following two features. First, analytical subcontractors were
required to analyze each field sample for all targeted sub-
stances, and were also required to identify the next 20 most
abundant substances found in the sample. Second, EPA conducted
an audit of the results obtained by analytical subcontractors, in
order to determine the accuracy of substance identifications and
completeness of substance identifications in those field samples
analyzed by the subcontractors. The results of the audit, re-
ported in Appendix F of this Volume, provided additional confirm-
ation of the validity of the analytical chemistry data presented
in this report.
12
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1.1.5 Sampling Procedures and Sites Sampled
A total of 174 ground-water monitoring wells were installed
by EPA at Love Canal and at control sites. Samples of ground
water were obtained from 136 of the monitoring wells. The re-
maining 38 wells were either dry or the sample results were
rejected by the data validation and QA/QC process.
Two separate ground-water systems exist in the Love Canal
area and were monitored individually. A shallow overburden sys-
tem was often encountered, usually at a depth of less than 20
feet below the land surface. Wells installed to monitor the
shallow system were referred to as "A Wells." Ground-water sam-
ples collected from a total of 79 A Wells are included in the
validated data base. The major aquifer present in the Love Canal
area is located in the underlying Lockport Dolomite bedrock, a
unit that was encountered typically at a depth of approximately
40 feet below the land surface. The major water bearing zone of
the dolomite was found to occupy approximately the top 20 feet of
the unit. The bedrock aquifer was sampled separately through the
installation of bedrock wells, referred to as "B Wells." Ground-
water samples collected from a total of 57 B Wells are included
in the validated data base. Most sites sampled had both A and B
Wells installed.
A large number of other water samples were collected at Love
Canal. These included: (1) residential drinking water (including
both raw and finished water samples collected from the Niagara
Falls Drinking Water Treatment Plant); (2) sanitary sewer water;
(3) storm sewer water; (4) sump water; and (5) surface water from
area creeks and rivers (sites in or near to the Declaration Area
were usually located in proximity to storm sewer outfalls). A
full enumeration of the number of water sampling sites that are
represented in the validated data base is given in Table 2.
A total of 171 soil sampling sites are represented in the
validated data base. The procedure used for collecting soil sam-
ples was designed to maximize the probability of detecting the
subsurface migration of chemicals through soils. Because it was
not possible to stipulate the soil depth at which leachate might
move laterally from Love Canal, and/or percolate downwards
through soils, the more permeable top 6 feet of soil was sampled.
At each soil sampling site a total of 7 soil cores, each 6 feet
long and 1 3/8 inches in diameter, were collected following a
pattern (typically a circular shape) that was representative of
the physical area sampled. Two of the seven soil cores were ana-
lyzed for the presence of targeted "volatile" compounds. The re-
maining five soil cores were composited and analyzed for addi-
tional targeted substances. A full enumeration of the number of
soil sampling sites that are represented in the validated data
base is given in Table 2.
13
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TABLE 2. A SUMMARY OF LOVE CANAL SITES SAMPLED AND REPRESENTED
IN THE VALIDATED DATA BASE
Sampling Areas
/"•«.-, .-,,3
Water
Drinking
Ground: A Wells
B Wells
Sanitary sewer
Storm sewer
Sump
Surface
Soil
Sediment
Sanitary sewer
Storm sev?er
Stream
Sump
Air
Basement
Living
Outside
Transport study
Occupied/
Unoccupied study
Sump/Basement-
Air study
Biota
Crayfish
Dog hair
Maple leaves
Mice
Oatmeal
Potatoes
Worms
1-10
31
49
29
1
22
33
4
112
1
18
4
—
9
55
8
—
3
0
1
20
14
5
12
11
4
11
3
19
13
0
3
13
—
24
0
4
—
3
1
6
1
—
0
9
^
—
6
2
2
2
2
99
5
11
15
0
1
1
5
9
0
1
5
—
0
4
0
—
0
0
1
15
11
2
4
3
3
Sub-Total
39
79
57
1
26
47
9
145
1
23
9
3
10
65
9
—
3
9
2
35
31
9
18
16
9
97 98 Total
5 — 44
79
57
_ — 1
•— -™ X
2 — 28
7 — 54
10 — 19
28 — 171
1
1 — 24
9 — 18
__ q
10
65
9
5 5
4 — 7
9
__ __ 2
35
21
_ _ ___ Q
18
16
g
Note: Dashes signify not applicable
14
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Sediment samples were collected from a number of different
sources during the Love Canal monitoring program. Sediment sam-
ples were collected from area creeks and rivers, in conjunction
with the collection of surface-water samples. As was noted
earlier, sites in or near to the Declaration Area were usually
located in proximity to storm sewer outfalls. In addition, sedi-
ment samples were collected, as available, from the following
sources: (1) sanitary sewers; (2) storm sewers; (3) sumps; and
(4) from the on-site Leachate Treatment Facility located adjacent
to the former canal on 97th Street. A full enumeration of the
number of sediment sampling sites that are represented in the
validated data base is given in Table 2.
In addition to the organic and inorganic chemicals routinely
determined in water/soil/sediment samples, EPA conducted a moni-
toring program to define and quantify the radionuclides present
in the general Love Canal area. Those radionuclides analyzed for
by EPA included all gamma-emitting radionuclides and, in drinking
water samples, tritium.
Air monitoring at Love Canal was conducted in 65 continuously
unoccupied residences. In each of these residences, living area
air was monitored by means of collecting integrated 12-hour sam-
ples using the sorbents TENAX and polyurethane foam (PFOAM). A
maximum of 13 daytime (6 a.m. to 6 p.m.) air sampling campaigns
were conducted in each of these residences throughout the dura-
tion of the monitoring program. In addition to the normal day-
time sampling campaigns, 3 nighttime campaigns (also of 12 hours
duration) were conducted in some of these same residences. Each
sampling area contained from four to eight living area air moni-
toring sites.
In 9 of the 65 air monitoring sites, basement air and outdoor
(ambient) air were also monitored using the sorbents TENAX and
PPOAM. In addition, outdoor sampling sites were monitored with
high-volume (HIVOL) particulate samplers, which were started si-
multaneously with the TENAX and PFOAM samplers, and were operated
for 24-hour periods. Air samples from basement and outdoor loca-
tions were collected in synchronization with the 13 regularly
conducted living area air sampling campaigns.
Residences in which multiple air sampling locations were es-
tablished were referred to as "base" residences. At each base
residence, efforts were made to sample all environmental media
and usually included indoor and outdoor air, ground water from
both A and B Wells, drinking water, sump water, soil, and food-
stuff introduced to the residence as part of the limited biologi-
cal monitoring program conducted at Love Canal. All sampling
areas immediately adjacent to the former canal contained one base
residence. Due to limited availability of appropriate locations
and residential structures, it was not possible to secure a
15
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control site that satisfied the requirements established to
designate it a base residence.
Three special air monitoring research studies were also
conducted at Love Canal. These studies involved an investigation
of the airborne transportation of pollutants in the Niagara Falls
area, the effects of domiciliary occupancy on indoor air pollu-
tion levels, and an examination of the interrelationship between
contaminant concentration levels in basement sumps and basement
air.
An enumeration of the number of air monitoring sites that are
represented in the validated data base is given in Table 2.
A limited biological sampling program was conducted by EPA at
Love Canal for the purpose of investigating the use of local
biological systems to monitor the biological availability and bi-
ological accumulation of substances found in appropriate environ-
mental media. The biota program involved the collection and
analysis of a limited number of samples, including: (1) crayfish
(40 composite samples); (2) domestic dog hair; (3) silver maple
leaves; (4) field mice {100 samples); and (5) common earthworms
(30 samples); as well as (6) purposely introducing foodstuff
(oatmeal and potatoes) into the basements of base residences to
determine their potential for accumulation of volatile organic
compounds. The biological monitoring program was intentionally
not directed at attempting to determine health or ecological ef-
fects of toxic chemicals in biota. A full enumeration of the num-
ber of biota sampling sites (approximately commensurate with the
number of samples except for crayfish, mice, and earthworms) that
are represented in the validated data base is given in Table 2.
1.1.6 Limitations
Even though EPA conducted a major sampling effort at Love
Canal, resulting in the acquisition of a considerable amount of
environmental monitoring data, it is acknowledged that the pro-
ject was conceived, initiated, and conducted under severe bud-
getary and time constraints. It was recognized, however, that
the critical nature of the problem at Love Canal, involving a
large number of nearby residents, meant that the monitoring pro-
gram conducted by EPA had to be initiated quickly, be thorough,
and of high quality. Consequently, a number of decisions were
made by EPA, concerning the design and conduct of the monitoring
studies, that have potential influence on the interpretation of
the study findings.
First, due to the size of the geographical area involved, a
statistical survey design was formulated to determine the extent
and degree of environmental contamination in the Declaration Area
that was directly and incrementally attributable to the migration
of toxic substances from Love Canal. Thus, for each environmental
16
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medium monitored, a sampling design with an appropriate sampling
frame was employed for site selection. In all media, the sam-
pling design used combined aspects of both purposive selection
(for example, intentionally locating some sampling sites to
maximize the probability of detecting chemicals that had migrated
from Love Canal), and simple random sampling. Whenever possible,
sampling sites were stratified according to geographical areas
that were defined by natural or manmade physical boundaries, in
order to facilitate the identification of potential spatial
variability in contamination levels in the Declaration Area.
Second, a finite (but large) list of targeted substances was
identified for monitoring in each environmental medium sampled.
Third, because a state of emergency existed at Love Canal, a
3-month time constraint (as opposed to 6 months, 1 year, or long-
er) was imposed on sampling. While this time frame limited the
scope of the investigation, it still provided substantial infor-
mation regarding potential environmental contamination hazards in
the Declaration Area resulting directly from Love Canal.
Fourth, all routine living area air monitoring residences
had to be unoccupied continuously throughout the study period, in
order to control for the potentially confounding effects of
household activities on indoor air pollution levels. By repeti-
tively monitoring air, a 3-month time series of data was obtained
that incorporated the potential for detecting temporal trends
(for example, trends due to changes in temperature, humidity,
precipitation, and wind direction) in concentration levels, and
were sampled repetitively.
Fifth, all EPA sampling activities at Love Canal were depen-
dent on the cooperation and willingness of area residents (and
state and local authorities) to grant EPA written permission to
sample on their property. In recognition of the importance of the
EPA monitoring program to each individual, a high rate of cooper-
ation (in excess of 90 percent) was generally displayed by Decla-
ration Area residents.
Partially due to these factors, the ability to use the find-
ings of the EPA monitoring program to predict future weather-
influenced conditions at Love Canal may be limited. In similar
fashion, the statistical limitations and uncertainties associated
with all sampling designs (in contrast to a complete census in-
volving environmental monitoring at all residences), are acknowl-
edged. Consequently, any attempt to infer prior conditions in
the Declaration Area (such as air pollution levels) from the cur-
rent environmental monitoring data is risky and has not been per-
formed.
17
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1.2 RESULTS
The EPA ground-water monitoring program revealed no evidence
of contamination attributable to Love Canal in the bedrock aqui-
fer and only very localized contamination in the shallow system.
In general, evidence of contaminated ground water that was di-
rectly attributable to the migration of substances from the for-
mer canal was found only in a few shallow system A Wells located
immediately adjacent to Love Canal in the residential lots of
some ring 1 houses. Clear evidence of ground-water contamination
directly attributable to Love Canal was not found outside of the
area around ring 1 houses or in the Declaration Area.
On the basis of tests conducted in monitoring wells, and a
ground-water flow model constructed specifically according to hy-
drogeologic conditions encountered at Love Canal, it was deter-
mined that the barrier drain system (the Leachate Collection Sys-
tem) was functioning effectively. The barrier drain system was
installed completely around Love Canal by the City of Niagara
Palls and the State of New York in 1978 and 1979, as a contain-
ment remedy designed to halt the lateral migration of chemicals
through the soil. In addition, a clay cap was placed on the
landfill. The EPA findings suggested that the barrier drains
were operating to intercept chemicals which might be migrating
laterally from the former canal, to lower the hydraulic head in
the former canal (preventing a so-called "bathtub overflow"
effect), and to move nearby ground water towards the drains for
collection and subsequent treatment. As a result of the draw-
back influence of the barrier drains, which extend approximately
1,700 feet in the more permeable sandy soils and 180 feet in the
less permeable clays found in the area, nearly all nearby shallow
system contamination should be recovered (assuming no additional
attenuation of contaminants) that resulted from the prior mi-
gration of contaminants out of Love Canal.
The soil monitoring program yielded results that were consis-
tent with the ground-water monitoring findings. In particular,
clear evidence of soil contamination attributable to Love Canal
was found only in the yards of a relatively few ring 1 houses,
and tended to coincide with those sampling sites where contami-
nation was also found in shallow system A Wells. The soil find-
ings suggested that the consistent multimedia pattern of environ-
mental contamination observed at certain ring 1 locations was due
to the presence of local, highly heterogeneous soil conditions
that permitted the relatively more rapid migration of contami-
nants from Love Canal to those locations. In particular, soil
contamination directly attributable to the migration of contami-
nants from Love Canal was found to be confined to ring 1, and was
associated with the discrete presence of sandy soil (for example,
in the form of a sand lens), and with the relative abundance of
more permeable fill materials (for example, filled swales). No
evidence of soil contamination outside of ring 1 was found in
18
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support of the hypothesis that swales served as preferential
routes of chemical migration from Love Canal. Furthermore, no
patterns of soil contamination were found outside of ring 1, and
no clear evidence of soil contamination was found in the Declara-
tion Are.a, that could be directly attributed to the migration of
contaminants from Love Canal.
Evidence of contamination in sump water and sump sediment
samples was found in relatively few ring 1 houses. The ring 1
sites at which sump contamination was found tended to coincide
with, or be located near to, those sites where contamination was
found in shallow system A Wells and in soil samples. These sites
were located mainly south of Wheatfield Avenue and on the 97th
Street (west) side of Love Canal. Relatively high levels of con-
taminants were found in the few ring 1 sumps that contained an
amount of sediment adequate for separate sampling and analysis
purposes. No pattern of sump contamination was found outside of
ring 1 houses, and no clear evidence of sump contamination was
found in the Declaration Area that could be directly attributed
to the migration of contaminants from Love Canal.
Samples of storm sewer water and sediment revealed that high-
ly contaminated sediment and contaminated water were traceable
from the Canal Area to local outfalls, and that approximate con-
centration gradients (for certain compounds) corresponding to
storm-water flow directions existed. Because of the remedial ac-
tions taken at the site (and based on the findings of the hydro-
geologic program), it is likely that only residual (that is,
prior to remedial construction) contamination was found in the
storm sewer lines. Furthermore, it is possible that the contami-
nation found in the storm sewer lines near Love Canal resulted
from the following; (1) infiltration of the storm sewer laterals
on Read and Wheatfield Avenues that were connected (respectively)
to the northward and southward flowing storm sewer lines on 97th
Street, and the storm sewer lateral on Wheatfield Avenue that was
connected to the southward flowing storm sewer line on 99th
Street; (2) historical (that is, prior to remedial construction)
overland flow of contaminated surface water and sediment that
would have been collected by curb drains on all streets immedi-
ately adjacent to or crossing the former canal; (3) a catch basin
and drain that was located near the former canal in the backyard
of houses at 949-953 97th Street, and which emptied into the 97th
Street northward flowing storm sewer line; and (4) by the dis-
charge of contaminated water and sediment that was taken-up by
the no longer operating sump pumps located in the basements of
certain ring 1 houses, and discharged into the 97th and 99th
Streets storm sewer lines.
19
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Because of the relatively low solubility in water of many of
the organic compounds monitored, and the continuing flow of water
through the storm sewer lines, the concentration levels of organ-
ic compounds detected in storm sewer sediment samples were gener-
ally higher (due to certain organic compounds being more readily
sorbed on sediment particles) than corresponding concentrations
in storm sewer water samples. It should also be noted that sedi-
ment samples could not be collected at all storm sewer sites sam-
pled, and that sediment tended to be more readily available for
collection at storm sewer line junctions and turning points.
Surface-water samples and sediment samples collected from
Love Canal area creeks and rivers revealed highly contaminated
sediment and contaminated water in the general vicinity of those
storm sewer outfall locations that were fed by lines connecting
to the 97th and 99th Streets storm sewers. In particular, the
sediment samples collected in Black Creek near the 96th Street
storm sewer outfall revealed that high levels of toxic organic
compounds were present, as did sediment samples collected in the
Niagara River near the 102nd Street storm sewer outfall. Due to
the close proximity of the 102nd Street landfill to water and
sediment sampling sites in the Niagara River, it was not possible
to unequivocally identify the source(s) of contaminated Niagara
River sediment near the 102nd Street outfall.
The air monitoring program results were consistent with the
findings obtained from monitoring other environmental media. In
essence, indoor air contamination levels were elevated in a few
ring 1 houses, namely those houses where other media monitoring
efforts (for example, the special sump/basement air monitoring
study) also identified the presence of contaminants that had
migrated from Love Canal. Outside of the relatively few ring 1
houses so affected, no pattern of regular (living area) indoor,
or basement air contamination was observed. Furthermore, no clear
evidence of air pollution was found in the Declaration Area that
could be directly attributed to contamination emanating from Love
Canal.
The three special air monitoring research studies conducted
at Love Canal provided limited evidence of the following results.
First, airborne contaminants detected indoors were also detected
in the outside ambient air, and may have been transported from
upwind sources. Second, activities associated with domiciliary
occupancy suggested that such activities could potentially in-
crease indoor air pollution levels. And third, highly contamina-
ted sumps (which were found in only a limited number of ring 1
residences) could serve as potential contributing sources of high
levels of indoor air pollution.
20
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Analyses of drinking water samples revealed that the drinking
water sampled satisfied existing EPA drinking water quality
standards. Furthermore, no drinking water samples collected in
Declaration or Canal Area residences revealed the presence of
contamination that was directly attributable to Love Canal.
The results of monitoring for radioactive contaminants in
water/soil/sediment samples revealed that only normal background
radioactivity was present in the Declaration Area and in the
Canal Area. Analyses conducted indicated that the predominant
gamma-emitting radionuclides observed were naturally occurring
radionuclides such as radium-226 and the so-called daughter pro-
ducts of its- radioactive decay. Water samples analyzed revealed
that no gamma-emitting radionuclides were present above back-
ground levels, and drinking water concentrations of tritium were
well below the EPA drinking water standard. Soil and sediment
samples analyzed revealed the presence of only low levels of
naturally occurring radionuclides such as potassium-40 and the
daughter products of radium-226 and thorium-232, and low concen-
trations of cesium-137 comparable to worldwide fallout levels.
The limited biological monitoring program provided results
that were consistent with the findings obtained from environ-
mental monitoring activities. In general, no evidence of either
biological availability or biological accumulation of environ-
mental contaminants was observed among the species sampled in the
Declaration Area that could be attributed directly to environ-
mental contaminants that had migrated from Love Canal.
Finally, the results of a special monitoring program for the
highly toxic compound 2,3,7,8-tetrachlorodibenzo-p-dioxin (2,3,
7,8-TCDD), revealed evidence of limited environmental contami-
nation in the general Love Canal area. In particular, it was
determined that 2,3,7,8-TCDD was present: (1) in the untreated
leachate sampled at the Leachate Treatment Facility (but was not
detected in the treated effluent); (2) in the sumps of certain
ring 1 residences (sumps that also contained high concentrations
of numerous other chlorinated organic compounds); and (3) in
sediment samples collected from certain storm sewers that origi-
nated near the former canal, and in sediment samples collected
from local creeks and the Niagara River near the outfalls of
those storm sewers (sediments that also contained high concen-
trations of numerous other chlorinated organic compounds). These
results for 2,3,7,8-TCDD at Love Canal both confirmed and exten-
ded the findings reported publicly in 1980 by NYS.
1.3 CONCLUSIONS
The results of the EPA multimedia environmental monitoring
program conducted at Love Canal during the summer and fall of
1980 revealed a limited pattern of environmental contamination
21
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restricted mainly to the immediate vicinity of the inactive haz-
ardous wastes landfill. The data suggested that localized and
highly selective migration of toxic chemicals through soils had
contaminated a few ring 1 houses located mainly south of Wheat-
field Avenue. The data also revealed that substantial residual
contamination was present in those local storm sewer lines origi-
nating near the former canal, and was also present in the surface
water and sediment of area creeks and rivers at locations that
were near to and downstream from the outfalls of those storm
sewer lines.
Apart from these findings, the Declaration Area exhibited no
clear evidence of Love Canal-related contamination in any envi-
ronmental medium monitored. Also, in all media monitored, the
data revealed that the occurrence and concentration levels of
monitored substances observed in the Declaration Area could not
be attributed in a consistent fashion to the migration of contam-
inants from Love Canal. The data also provided no evidence sup-
porting the hypothesis that (outside of ring 1) swales may have
served as preferential routes for chemicals to migrate from the
former canal. Finally, the data suggested that the barrier drain
system surrounding the landfill was operating effectively to in-
tercept the lateral migration of contaminants from Love Canal,
and was also drawing near-surface ground water back to the drains
for collection and decontamination at the onsite Leachate Treat-
ment Facility.
The patterns of environmental contamination discovered at
Love Canal, that could be attributed directly to the migration of
contaminants from Love Canal, were found to be consistent with
the geology of the site. Because of the naturally occurring
clayey soils in the general Love Canal area, the rapid and dis-
tant migration of substantial amounts of contaminants from the
former canal to surrounding residences is highly unlikely.
Migration of contaminants from Love Canal was found to have
occurred over relatively short distances, probably through selec-
tive soil pathways consisting of more permeable materials, and
was confined to ring 1 of the Canal Area. Even though the trans-
port of contaminants was greater in the more permeable soils, the
random deposition and apparent discontinuity of these soils made
it highly doubtful that much contamination outside of ring 1 had
occurred by ground-water transport.
22
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CHAPTER 2
BACKGROUND
In order to understand the events leading to the May 21, 1980
emergency declaration order and to better understand the context
in which the EPA Love Canal study was conducted, a brief review
of the major historical developments pertaining to use of the
Love Canal site is presented.
2.1 SITE LOCATION
The Love Canal Declaration Area is located in the southeast-
ern portion of the La Salle section of the City of Niagara Falls,
New York close to the corporate boundary of the Town of Wheat-
field (Figure 1). The inactive hazardous wastes landfill known
as Love Canal physically occupies the central 16-acre portion of
the rectangular plot of ground bounded by Colvin Boulevard on the
north, 99th Street on the east, Frontier Avenue on the south, and
97th Street on the west. Two roads, Read and Wheatfield Avenues,
cross the landfill in an east-west direction. A public elementary
school, known as the 99th Street Elementary School, occupies a
portion of the land between Read and Wheatfield Avenues and was
built adjacent to the eastern boundary of the landfill. The
southernmost portion of the site is approximately 1,500 feet
north of the Niagara River. Another inactive hazardous wastes
site, known as the 102nd Street landfill, is located to the south
of Love Canal and is approximately bounded by the following:
Buffalo Avenue on the north; the Niagara River on the south; and
lines that would be formed on the east by extending 102nd Street
to the Niagara River, and on the west by extending 97th Street to
the Niagara River.
The area encompassed by the May 21, 1980 state of emergency
order, and the focus of the EPA Love Canal investigations, was
the area previously identified as "DECLARATION AREA" in Figure 2
and referred to in this report as the Declaration Area. The area
identified with the legend "CANAL AREA" in Figure 2 (referred to
in this report as the Canal Area) depicts the location of the in-
active landfill, and included nearly all of the houses that were
acquired and evacuated by the State of New York in 1978. The
boundaries of the Declaration Area corresponded roughly to the
following streets and features identified in Figure 3: Bergholtz
23
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Creek on the north; 102nd Street on the east (and its imaginary
northward extension to Bergholtz Creek); 103rd Street on the
southeast; Buffalo Avenue on the south; and 93rd Street on the
west. The residences on the west side of 93rd Street and on the
east side of 102nd and 103rd Streets were included in the state
of emergency order and in the Declaration Area.
2.2 SITE HISTORY
In the early 1890's an entrepreneur named William T. Love en-
visioned the founding of a planned industrial community that he
named Model City, to be located north of Niagara Falls in the
present town of Lewiston, New York. Love's plan was to dig a ca-
nal diverting water from the Niagara River northward to the Niag-
ara escarpment in order to economically produce hydroelectric
power for the industries that Love hoped to lure to Model City.
Work began on the canal on May 23, 1894 in the La Salle section
of Niagara Falls. The canal was located in a 400-foot wide
right-of-way and according to newspaper reports was to be 80 feet
wide at the top, 30 feet deep, and 40 feet wide at the base. Ap-
parently, due to the joint occurrence of a financial depression
in the 1890's and the development of a practical means for gen-
erating alternating current by Nikola Tesla (1856-1943), which
permitted the economical transmission of electrical power over
long distances, Love's dream of Model City, fueled by the natural
energy source of a power canal, soon evaporated.
While some uncertainty exists today as to both the originally
excavated depth and the southernmost extension of the former ca-
nal that bears Love's name, it is known from aerial photographic
evidence that in 1938 the portion of Love Canal bounded by Colvin
Boulevard, 99th Street, Frontier Avenue, and 97th Street was open
and filled to some depth with water. It is also known that exca-
vated soils were piled near the edge of the canal, forming mounds
estimated as 10 to 15 feet high in places.
In 1942 the company known today as Hooker Chemicals and Plas-
tics Corporation (Hooker) entered into an agreement with the Ni-
agara Power and Development Company (then owner of the canal) to
purchase Love's unfinished canal. Although Hooker did not actual-
ly acquire the property until 1947, Hooker acknowledged that it
used the canal between 1942 and 1953 for the disposal of at least
21,800 tons of various chemical wastes. A list of the types of
wastes buried in Love Canal is presented in Table 3.
According to NYS interpretations of aerial photographs taken
throughout the time period, Hooker apparently deposited chemical
wastes in the canal by first constructing dikes across the canal,
which formed impounded areas of water, and then filled the canal
on a section-by-section basis. It is not known how much, if any,
of the impounded water was drained from the canal prior to land-
filling operations.
24
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TABLE 3. CHEMICALS DISPOSED AT LOV1 CANAL BY HOOKER ELECTROCHEMICAL
COMPANY (1942-1953 )t
Physical
Type of Waste
Misc. acid chlorides other than
benzoyl--includes acetyl, caprylyl,
butyryl, nitro benzoyls
Thionyl chloride and misc.
sulfur/chlorine compounds
Misc. chlorination--includes
waxes, oils, naphthalenes, aniline
Dodecyl (Lauryl, Lorol) mercaptans
(DDM), chlorides and misc. organic
sulfur compounds
Trichlorophenol (TCP)
Benzoyl chlorides and benzo-
trichlorides
Metal chlorides
Liquid disulfides (LDS/LDSN/BDS)
and chlorotoluenes
Hexachlorocyelohexane
(r-BHG/Lindane)
Chlorobenzenes
State
liquid
and
solid
liquid
and
solid
liquid
and
solid
liquid
and
solid
liquid
and
solid
liquid
and
solid
solid
liquid
solid
liquid
and
solid
Total Estimated
Quantity
(Tons)
400
500
1,000
2,400
200
800
400
700
6,900
2,000
Container
drum
drum
drum
drum
drum
drum
drum
drum
drum and
nonmetallic
containers
drum and
nonmetallic
containers
'Benzylchlorides—includes benzyl solid
chloride, benzyl alcohol, benzyl
thiocyanate
Sodium sulfide/sulfhydrates solid
Misc. 10% of above
Total
2,400
2,000
2,000
21,800
drum
drum
TInteragency Task Force on Hazardous Wastes, Draft Report on Hazardous Waste
Disposal in Erie and Niagara Counties, New York, March 1979. Hooker Electro-
chemical Company is now known as the Hooker Chemicals and Plastics Corpora-
tion.
25
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The significance of the issue of whether or not water was
drained from impounded areas prior to Hooker dumping wastes in
the canal looms in potential importance when the topography of
the site is considered. Although the general Love Canal area is
quite flat, the region was traversed by a number of naturally oc-
curring shallow (less than 10 feet deep) surface depressions,
sometimes called swales, that served as preferential pathways of
surface-water runoff. Some of the swales, which are now all
filled, were intersected during excavation of the canal. The wavy
lines superimposed on Figure 2 illustrate the approximate loca-
tion of known former swales in the general vicinity of Love
Canal.
It has been offered by others that Hooker's active landfill-
ing operations may have displaced impounded water, potentially
contaminated with toxic chemicals, into the drainage pathways. In
addition, if the open swales were later filled with rubble and
more permeable sandy-soils during residential constuction, then
leachate may have preferentially migrated from the landfill
through the filled swales to nearby houses. The EPA monitoring
program was designed to test the validity of this hypothesis.
It is also known that the City of Niagara Falls disposed of
solid wastes (mainly in the portion of the canal bounded today by
Read and Wheatfield Avenues) in Love Canal. No other source of
wastes disposed of in the canal has yet been identified.
Shortly after Hooker terminated disposal activities at Love
Canal in 1953 the land was acquired for the purchase price of
$1.00 by the Niagara Falls Board of Education for the purpose of
constructing an elementary school on the site. In 1955 the 99th
Street Elementary School, located adjacent to the eastern edge of
the landfill on 99th Street between Read and Wheatfield Avenues,
was completed and opened. A French drain system was installed
around the school at the time of construction and was connected
at some later time to a storm sewer line on 99th Street.
As early as 1938, a number of private residences were located
near the northeast corner of Love Canal. By 1952 approximately 6
to 10 houses existed on 99th Street (the backyards of these hous-
es faced toward the active dumping in the canal), mainly located
around the central and south-central portions of the canal. By
1972 virtually all of the 99 houses on 97th and 99th Streets
whose backyards faced the former canal, the so-called ring 1
houses, were completed. In general, residential development
around Love Canal occurred primarily from the mid-1950's through
the early 1970"s. By 1966, all evidence of earlier excavation at
the site had been eliminated by subsequent construction activi-
ties .
26
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Shortly after the canal was filled in 1953, Read and Wheat-
field Avenues were built across the landfill. Anecdotal reports
by area residents relate that chemical wastes, fly ash, and muni-
cipal refuse were encountered during the construction of these
streets. In 1957 the City of Niagara Falls installed a sanitary
sewer line across the former canal under Wheatfield Avenue. The
sewer pipe was laid approximately 10 feet below the surface of
Wheatfield Avenue. Contrary to specification documents, which
stipulated that the sewer pipe be encircled with gravel, field
inspection notes compiled by the State of New York Department of
Environmental Conservation (NYS DEC) reported that only excavated
soils were used to backfill the trench.
In 1960 the City of Niagara Falls installed a storm sewer
line under Read Avenue, entering from 97th Street and ending in a
catch basin located approximately midway between 97th and 99th
Streets. Field inspection notes (NYS DEC) once again reported
that only excavated soils were used to fill the trench. Although
city records do not identify the construction of storm sewer lat-
erals on Wheatfield Avenue, connecting to storm sewer lines on
97th and 99th Streets, field inspection notes (NYS DEC) reported
that storm sewer laterals were built at some time on Wheatfield
Avenue entering from both 97th and 99th Streets and each running
towards the former canal for approximately 170 feet. As with
other sewer lines installed by the City of Niagara Falls around
Love Canal, these too were reportedly (NYS DEC) backfilled with
excavated soils.
As early as 1966 a little league baseball diamond was located
on the northern portion of Love Canal just south of Colvin Boule-
vard. In 1968 the La Salle Expressway was constructed north of
Buffalo Avenue. The construction of this four-lane divided high-
way required the relocation of Frontier Avenue approximately 50
feet northward. During the relocation of Frontier Avenue, chemi-
cally-contaminated soils and drummed wastes were encountered. \t
the request of the State of New York Department of Transportation
(DOT), Hooker agreed to remove 40 truckloads of wastes and soil.
At the same time that Frontier Avenue was relocated, the storm
sewer line under Frontier Avenue was also relocated by DOT.
Field inspection notes (NYS DEC) reported that the storm sewer
line installed by DOT was constructed according to specifications
and encircled with gravel prior to backfilling the excavation
trench.
As a result of unusually high precipitation in 1975 and 1976,
a very high ground-water level apparently developed in the gener-
al Love Canal area. At about this time a number of problems be-
came markedly noticed by Love Canal residents, namely: (1) por-
tions of the landfill subsided and drums surfaced in a number of
locations? (2) ponded surface water, heavily contaminated with
27
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chemicals, was found in the backyards of some ring 1 "houses; (3)
unpleasant chemical odors (caused by the volatilization of sur-
faced chemical wastes) were cited by residents as a factor con-
tributing to both discomfort and illnesses; (4) evidence of
through-ground migration of toxic chemicals became apparent in
the basements of some ring 1 houses with the appearance of a
noxious, oily residue accumulating in basement sumps, the cor-
rosion of sump pumps, and the physical evidence of chemical in-
filtration through cinder-block foundations? and (5) noxious
chemical fumes were noticed emanating from several near-by storm
sewer manhole covers.
By November of 1976, the frequency and magnitude of the prob-
lems at Love Canal cited by area residents prompted a meeting of
local, state, and federal officials where it was agreed that NYS
DEC would conduct and be responsible for an investigation of the
site, and that EPA would provide technical assistance. During the
subsequent year, a number of environmental samples were collected
in ring 1 houses and at the 99th Street Elementary School.
Partially as a result of these investigations, Commissioner
Robert P. Whalen of the State of New York Department of Health
(DOH) in April of 1978 declared the site to be a threat to health
and ordered that the area nearest the landfill be fenced. In June
1978 NYS DOH initiated a house-to-house health survey and col-
lected air samples in ring 1 houses. After reviewing all avail-
able Love Canal data, Commissioner Whalen declared a health emer-
gency at Love Canal on August 2, 1978. The order issued by Whalen
resulted in, among other things, the closing of the 99th Street
Elementary School and a recommendation for the temporary evacua-
tion of pregnant women and all children under the age of 2 who
resided in the first two rings of houses around the former canal.
On August 7, 1978 Governor Carey announced that NYS would
purchase (at full replacement value) all ring 1 houses at Love
Canal. This announcement of the permanent relocation of Love Ca-
nal residents was subsequently expanded to include all 238 rings
1 and 2 houses. On the same date, President Carter issued an
order declaring that a state of emergency existed in the southern
portion of Love Canal, where contamination was at its worst lev-
el, enabling the use of federal funds and the Federal Disaster
Assistance Agency to aid the City of Niagara Falls in providing
remedies at the site.
During the latter part of 1978 and through the spring of 1979
the City of Niagara Falls (partly with the aid of federal funds)
designed and constructed a barrier drain system parallel to, and
on both sides of, the southern portion of Love Canal. The bar-
rier drain system installed by the City of Niagara Falls was es-
sentially a French drain containing perforated tile-pipe. The
perforated tiles were buried in a trench 12 to 15 feet in depth,
-------
covered with 2 feet of uniformly sized gravel, and then back-
filled with sand. Initially, leachate collected from the land-
fill was treated onsite by an EPA mobile activated-carbon filter
system. Subsequently, a permanent activated-carbon Leachate
Treatment Facility (partially financed by an EPA cooperative
agreement with NYS DEC) was constructed near the northeast corner
of 97th Street and Wheatfield Avenue. The Leachate Treatment Fa-
cility became operational at the end of 1979.
In the spring of 1979, NYS DEC assumed responsibility for the
construction of additional portions of the barrier drain system
in the central and northern sections of Love Canal. The portions
of the barrier drain system constructed by DEC were connected to
the southern system, and included a complete encircling of the
former canal in the north (south of Colvin Boulevard) and in the
south (approximately located in the center of Frontier Avenue).
In the north, the drains were located in trenches up to 18 feet
in depth. Figure 5 illustrates the approximate location of the
entire barrier drain system installed at Love Canal by the City
of Niagara Falls and NYS DEC. The entire DEC project was complet-
ed by the end of 1979, with contract costs totalling more than
$13 million (including construction of the Leachate Treatment
Facility).
The purposes of the remedial construction at Love Canal were
many. First, a leachate collection system was installed around
the entire perimeter of the former canal in order to prevent con-
tinuing lateral migration of contaminants from the landfill.
Second, lateral trenches were dug from the main barrier drain
-trench towards the former canal and filled with sand to hasten
dewatering of the site and to facilitate construction. And
third, a relatively impermeable clay cap was installed over the
landfill to minimize volatilization of contaminants, prevent
human contact with hazardous wastes, prevent runoff of contami-
nated surface water, and to minimize the amount of precipitation
infiltrating the landfill and thus reduce the generation of
leachate. In Figure 6 a cross section of the former canal and
the barrier drain system are illustrated, along with an identifi-
cation of the general soil units (and their permeabilities) that
exist in the area.
It should be pointed out that access to the Canal Area and
the landfill has been restricted to the general public since
1979. Public access to the site was eliminated by the erection
of an 8-foot high cyclone fence around the entire area; for se-
curity purposes, the Canal Area is also patrolled. In Figure 5,
the approximate location of this fence around the site was iden-
tified. The reason the fence does not restrict access to all of
99th Street is due to the presence of two families (as of Feb-
ruary 1982) who still reside on the east side of 99th Street, and
have declined to sell their homes to the State.
29
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U)
o
D D D D O O O D O D D O D D O O O O O D D DP D
DnaDDDDaaDoooa
97th STREET
0130000000000
00000 0000
0000000000000
0000000000000
DDDDDDDDDDDDDDD
3 99th STREET
ui
I
DDaODDDDDDDDDD ODDDOD
L
DOG DO DD
KEY:
CANAL BOUNDARY o MANHOLES
BARRIER DRAINS, LATERALS ® WETWELLS (WITH MANHOLE)
•— FORCEMAINS • LYSIMETERS
•— GRAVITY MAIN-PARALLELS WEST BARRIER DRAIN C3 1st RING OF HOMES
— 8-FOOT HIGH CYCLONE FENCE a 2nd RING OF HOMES
(A) PERMANENTLEACHATE
TREATMENT FACILITY
@ UNDERGROUND LEACHATE STORAGE
C5) 99th STREET SCHOOL
(ADAPTED FROM A FIGURE PREPARED BY THE NEW YORK STATE
DEPARTMENT OF ENVIRONMENTAL CONSERVATION. USED BY PERMISSION)
Figure 5. Love Canal Remedial Action Project Plan View (not to scale)
-------
CLAY CAP, 3ft. THICK (PERMEABILITY: W7amM
PERMEABILITY:
1Q"7to1Q"8cm/i
SILT FILL-PERMEABILITY: >10"Bcm/i
SILTY SAND-PERMEABILITY: >Hr*em/i
BASEMENT
LOVE
CANAL ,r
OHIO. DEPTH I
FILL
COMPOSITION
AND DEPTH
UNKNOWN
GROUND LEVEL
1.8-2.5 ft.
4.0-5.5 ft
8.0ft.
12.0ft.
23.0 ft.
— 38.0 ft.
LEGEND: BURIED UTILITIES ARE
S - STORM SEWER
A - SANITARY SEW1R
W - WATER MAIN
Figure 6. Remedial Project: Transverse View
(Looking North from a Position Located
South of Wheatfield Avenue).
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During remedial construction the encountering of buried
wastes in the northwestern portion of the landfill necessitated a
westward extension of the barrier drain system on the 97th Street
side of the former canal between Read Avenue and Colvin Boule-
vard. During the construction of that portion of the barrier
drain system a catch basin was discovered near the former canal
boundary, along the property line between 949 and 953 97th Street
that had been installed by the City of Niagara Falls for the pur-
pose of draining the immediate area. The catch basin was found
to be connected to the 97th Street northward flowing storm sewer
line.
During the construction of the southern portion of the bar-
rier drain system three separate pieces of field tiles were dis-
covered. It was offered by local residents that at one time
these tiles were used to drain some property (or properties) east
of the site into the canal. These field tiles were documented in
NYS DOH field inspection notes as being located near the follow-
ing lots: 454 99th Street? north side of 474 99th Street; and on
the lot line between 474 and 476 99th Street. Both the catch
basin on 97th Street and the field tiles on 99th Street were
cut-off by installation of the barrier drain system.
After a yearlong investigation, the Department of Justice, on
behalf of EPA, filed a civil lawsuit against Hooker (and related
corporate defendants) on December 20, 1979 for improper hazardous
waste disposal at four Niagara Falls sites. The lawsuit alleged,
among other things, that Hooker had caused or contributed to the
creation of an "imminent and substantial endangerment" and a
nuisance at Love Canal.
In January 1980 EPA, at the request of the Department of Jus-
tice, contracted for a limited pilot cytogenetic assessment of 36
Love Canal residents for evidence-gathering purposes. The intent
of the study was twofold: first, to determine if excess chromo-
some damage was present among Love Canal residents,- and second,
to determine if the prevalence and severity of cytogenetic abnor-
malities detected warranted a full-scale investigation. On May
19, 1980 the results of the assessment were released.
From a scientific point of view, the EPA pilot cytogenetic
assessment suggested that the testing of additional Love Canal
residents was probably warranted. However, a great amount of
uncertainty as to the cause of the observed chromosomal abnormal-
ities remained. In particular, the lack of physical evidence
attributing (in a dose-response fashion) cytogenetic damage to
incremental exposure to toxic chemicals migrating directly from
Love Canal left the cause of the observed damage unknown. In ad-
dition, the personal health implications resulting from damaged
chromosomes remained unknown.
32
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Partially as a result of these events President Carter de-
clared on May 21, 1980 (for the second time) that a state of
emergency existed at Love Canal. This action led to the tempo-
rary relocation of those residents desirous of moving and to the
initiation of the EPA Love Canal environmental monitoring studies
described in this report. On June 10, 1980 EPA officials from the
Office of Monitoring Systems and Quality Assurance (OMSQA), went
to Love Canal to outline to area residents the nature of the en-
vironmental monitoring studies that EPA planned to conduct. EPA
field sampling activities at Love Canal began on August 8, 1980
and were concluded on October 31, 1980.
As was mentioned earlier, on October 1, 1980 a plan for the
permanent relocation of all desirous Love Canal emergency decla-
ration area residents was announced. This plan implemented the
Supplemental Appropriations and Rescission Act of 1980 (commonly
known as the Javits-Moynihan amendment), 94 Stat. 857, that au-
thorized the federal government to provide up to $15 million fi-
nancial assistance to the State of New York for the permanent
relocation of residents living in the Declaration Area. Partial-
ly as a result of this agreement an Agency of the State of New
York, the Love Canal Area Revitalization Agency (LCARA), under
the leadership of Mayor Michael C. O'Laughlin of Niagara Falls,
assumed the responsibility for acquiring the property of those
residents who desired to sell their property, and for relocating
renters in the La Salle Development and senior citizens area. In
addition, LCARA was given the responsibility for long term plan-
ning and revitalization of the general Love Canal area.
33
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CHAPTER 3
DESIGN OF THE
MONITORING STUDIES
The environmental studies initiated by EPA at Love Canal
were designed as an integrated multimedia (that is, air, soil,
sediment, water, and biota) monitoring program to characterize
the incremental extent and degree of chemical contamination in
the May 21, 1980 emergency declaration area directly attributable
to the migration of contaminants from the former canal. The use
of a multimedia data collection strategy was intended to permit
the evaluation of the importance of each of the media pathways
(environmental routes) througli which individuals might be exposed
to toxic substances, and permit an eventual assessment of total
incremental exposure.
3.1 OBJECTIVES
The general objectives of the multimedia study designed and
conducted by EPA at Love Canal were as follows:
1. To characterize in each medium sampled the incremental
extent and degree of environmental contamination in the
Declaration Area directly attributable to Love Canal»
2. To determine the presence and direction of ground-water
flow in the area, and evaluate the effectiveness of the
remedial construction performed at Love Canal.
3. To determine if swales, sewer lines, and other geological
features (for example, sandy soil deposits in the form of
sand lenses) had a significant effect on the migration of
toxic substances from the former canal.
4. To obtain measurements of environmental contamination.
5. To determine potential temporal variability in air con-
tamination levels and infer the causal mechanisms (for
example, changes in ambient temperature) influencing the
observed contamination patterns.
34
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6. To investigate the use of locally available biological
systems as potential indicators of contaminants present in
the environment.
7. To provide an assessment of the relative environmental
quality of the Love Canal emergency declaration area.
3.2 IMPLEMENTATION
The EPA studies were initiated by first identifying the data
requirements of the overall objectives and then designing data
collection mechanisms appropriate for such activities. Within
the overall limitations of time, budget, and feasibility, a mul-
timedia monitoring program was designed and implemented at Love
Canal. As was previously mentioned, the contract costs associated
with the Love Canal project were $5.4 million. GCA Corporation of
Bedford, Massachusetts was selected as the prime management con-
tractor. Other subcontractors involved in the study, and their
areas of involvement, are identified in Table 4. The EPA Nation-
al Enforcement Investigations Center (Denver, Colorado) provided
assistance and guidance to sampling personnel in health and safe-
ty related matters during the collection of field samples.
As was mentioned previously, the identification of chemicals
to be determined in field samples was accomplished by reviewing
all available data concerning the contents of the landfill, in-
cluding: (1) reviewing the list of chemical wastes that Hooker
reported to have buried in Love Canal (Table 3); (2) reviewing
the results of all known previous environmental monitoring stud-
ies performed at Love Canal (including those conducted by both
NYS DOH and EPA); and (3) through the analysis of air, liquid,
and sediment samples collected by EPA directly from the Leachate
Treatment Facility and directly from the barrier drain system at
Love Canal, prior to the initiation of EPA field sampling activi-
ties. As a result of these efforts, comprehensive lists of sub-
stances to monitor in water/soil/sediment/biota samples and in
air samples were derived. The two lists are presented in Appen-
dix A of this Volume.
At the outset of the monitoring program it was postulated
that chemicals in the former canal were likely to have selective-
ly migrated from the source according to environmental medium and
according to location in the landfill (due to highly heterogen-
eous soil conditions at the site), and in concentration levels
that decreased with increasing distance from Love Canal. In addi-
tion, it was also recognized: (1) that former swales may have
preferentially allowed the migration of chemicals from the site
(due to the possibility that materials used to fill the swales
had greater permeability than the surrounding natural soils); (2)
that residences located in historically wet areas (that is, with
35
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TABLE 4. IDENTIFICATION OF EPA LABORATORIES AND PROJECT
SUBCONTRACTORS
EPA Laboratories
Laboratory (Abbreviation) Activity
Environmental Monitoring and Q&/QC for water samples;
Support Laboratory, Cincinnati audit of gas chromatography/
(EMSL-Cin) mass spectrometry (GC/MS)
subcontractor analyses
Environmental Monitoring Systems Water monitoring; soil/sedi-
Laboratory, Las Vegas ment/biota monitoring and
(EMSL-LV) QA/QC? audit of GC/MS sub-
contractor analyses
Environmental Monitoring Systems Air monitoring and QA/QC for
Laboratory, Research Triangle Park air samples; contract super-
(EMSL-RTP) vision; data processing
Environmental Research Laboratory, Hydrogeologic program
Ada (ERL-Ada)
Environmental Research Laboratory, Audit of GC/MS subcontractor
Athens (ERL-Athens) analyses
Environmental Research Laboratory, Analysis of selected samples
Corvalis (ERL-Corvalis)
Environmental Research Laboratory, Analysis of selected samples
Duluth (ERL-Duluth)
Health Effects Research Laboratory, QA/QC for PFOAM samples?
Research Triangle Park (HERL-RTP) confirmation of TCDD results
Analytical Subcontractor Laboratories
Laboratory (Abbreviation) Type of Analysis
Acurex Corporation (ACEE) Organics in soil, sediment,
and water
Advanced Environmental Systems, TOX and TOC
Inc. (AES)
Battelle Columbus Laboratories Air volatile organics
(BCL, BCL2, BCL3)
Compuchem/Mead Technology Organics in soil, sediment,
Laboratories (CMTL) and water
(continued)
36
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TABLE 4 (continued)
Analytical Subcontractor Laboratories
Laboratory (Abbreviation) Type of Analysis
Energy Resources Company
(ERCO)
Gulf South Research Institute
(GSRI, GSLA, GSNO)
IIT Research Institute (IIT)
Midwest Research Institute
(MWRI)
PEDCo Environmental
(PEDC)
PJB/Jacobs Engineering Group
(PJBL)
Southwest Research Institute
(SWRI)
TRW, Inc. (TRW)
Wright State University (WSU]
Inorganics in soil, sediment,
and water
Air semi-volatile organics;
organics in soil, sediment,
and water
Air volatile organics
Organics in biota
Air volatile organics?
preparation of TENAX
cartridges
Organics in soil, sediment,
and water; inorganics in
soil, sediment, and water
Air semi-volatile organics;
organics in biota, soil,
sediment, and water? in-
organics in biota, soil, and
sediment; preparation of
polyurethane foam plugs
Organics in water
TCDD (Dioxin) determinations
Other Subcontractors
Organization
Activity
Empire Soils
Geomet Technologies
GeoTrans
JRB
Research Triangle Institute
Technos
Well drilling
Field sample collection
Ground-water modeling
Supervisory geologists
Provision of quality control
TENAX cartridges
Geophysical investigation
37
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standing surface-water problems) were also typically associated
with the presence of former swales; (3) that loceil creeks and
rivers may be contaminated and serve as additional sources of
human exposure; (4) that manmade construction activities (such as
streets and Utilities buried therein) may have had a major in-
fluence on the subsurface migration of toxic substances from the
former canal; and (5) that efficiency in statistically estimating
typical chemical concentration levels, and the mapping of concen-
tration isopleths in certain media, could be enhanced through
stratification of the Declaration Area into more compact sampling
areas (in order to increase intra-area environmental homogene-
ity) .
With these considerations in mind, the sampling area scheme
described previously, and schematically represented in Figure 4,
was superimposed on the Declaration Area. Within each sampling
area, for a variety of media, site selection occurred by both
simple random selection (that is, with equal probability), and
purposive selection. At nine residences, referred to as base
sites, extensive integrated multimedia environmental monitoring
was conducted. The purposive selection of sampling sites was
conducted with the intent of increasing the likelihood of detect-
ing transport pathways through which toxic contaminants may have
migrated into the Declaration Area from Love Canal.
It can be seen in Figure 4 that the distribution and location
of sampling areas around the Canal Area (area 11) was designed to
facilitate the estimation of concentration isopleths. In addi-
tion, it can be seen that nearly all sampling area boundaries
were coincident with existing physical boundaries, and that prox-
imity of residences to area creeks was also incorporated in the
design (area 4). In subsequent figures identifying media specific
sampling locations, it will be apparent to the reader that (for
relevant media) sites were often intentionally selected to permit
monitoring of former swales located throughout the area.
Efforts were made for all monitored medium/source/location
combinations to obtain control sampling sites that were selected
specifically for comparison purposes. As a matter of convenience
all control sites data were collected in one organizational sam-
pling area, area 99, and are reported in this fashion in Volumes
II and III of this report. It should be noted that the control
sites do not really represent a physically bounded area, but
rather are simply a collection of medium-specific sampling sites.
Due to the physical distance separating control sampling sites,
no specific control area could be identified in Figure 4. When-
ever possible, control sites are identified and included in sub-
sequent figures showing medium-specific sampling locations.
Special attention was given to selecting control site loca-
tions in the Niagara Falls area that were not influenced directly
38
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by Love Canal or any other known hazardous waste sites. The con-
trol sites were monitored to determine normal pollutant levels
found near to (but not influenced by) Love Canal. The relative
concentration differences found between the Declaration Area and
other areas of interest were determined by subtraction.
As was mentioned earlier, EPA responded to the requests of
local residents living outside the Declaration Area to collect
additional environmental samples. The results from these sampling
efforts were combined (in Volumes II and III) in one organiza-
tional sampling area, area 97. Also included in Volumes II and
III are data for sampling area 98. The data included in this
sampling area were obtained as part of the previously mentioned
ambient-air transport monitoring study, which was conducted to
determine the nature and amount of pollutants being transported
to the Declaration Area from sources other than Love Canal.
3.3 QUALITY ASSURANCE/QUALITY CONTROL (QA/QC) AND DATA VALIDA-
TION
Because QA/QC procedures form an integral part of any assess-
ment of the appropriateness and utility of the Love Canal data, a
brief discussion of certain QA/QC concepts, processes, and re-
sults is presented here. A more detailed discussion of medium-
specific QA/QC procedures and results may be found in Appendixes
C through E of this Volume. In addition, a comprehensive report
entitled Love CanalMonitoring Program,GCAQA/QC Summary Report,
describing the QA role and activities of the prime contractor
(GCA Corporation), may be obtained from the National Technical
Information Service (NTIS).
In response to the presidential order declaring a state of
emergency at Love Canal, and the great anxiety experienced by
local residents associated with this action, the monitoring pro-
gram devised by EPA was restricted to a 3-month sampling period.
Given this sampling-period time constraint, necessary cost con-
traints, and a directive to determine the extent and degree of
environmental contamination in the Declaration Area directly at-
tributable to the migration of contaminants from Love Canal, com-
prehensive medium-specific sampling designs were developed. The
major objective of the survey design was to collect and analyze a
statistically adequate number of samples to characterize accu-
rately Declaration Area contamination caused by Love Canal, and
to minimize the effects and uncertainties associated with the
constrained sampling time period. The analytical requirements
established by EPA were designed to complement the extensive sam-
pling programs. This was accomplished by targeting (using the
process described earlier) a relatively large number of sub-
stances to be determined in environmental samples. As a result
of these efforts, the likelihood was minimized that substantial
evidence of environmental contamination would be missed in the
Declaration Area samples collected.
39
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Given these general program requirements, analytical methods
were selected such that the following considerations were sat-
isfied. First, the shortness of the sampling time period (3
months), and the magnitude of the sampling program (more than
6,000 field samples were collected), necessitated the use of a
large number of analytical subcontractors. Typically, the quan-
tity of samples collected at Love Canal required that more than
one analytical subcontractor laboratory be used for each medium
sampled.
Second, the relatively large number of targeted organic com-
pounds to be determined in environmental samples, and the number
of analytical subcontractors needed to analyze the samples col-
lected, required the use of uniform analytical methods that had
the capacity for rapid sequential analysis of the large number of
organic compounds of interest at Love Canal.
Third, potential problems resulting from the organic analyti-
cal requirements of the program were minimized by selecting
(whenever possible) already existing analytical methods, in order
to take advantage of any prior experience that the subcontractors
may have had with the methods.
Fourth, the state of emergency at Love Canal precluded any
opportunity for formal multilaboratory testing of certain state-
of-the-art organic analytical methods selected for use during the
project.
Finally, in recognition of these factors, a primary goal of
qualitative accuracy for organic analyses (that is, correct iden-
tification of detected substances) was established. Consequently,
gas chromatographic/mass spectrometric (GC/MS) instrumentation
was selected for most organic analyses because it most completely
and reliably met the aforementioned requirements for the analysis
of targeted organic compounds in water, soil, sediment, and air
samples.
Given the constraints just enumerated, the primary objective
of the EPA Love Canal QA/QC program was to generate environmental
monitoring data that possessed the maximum accuracy, precision,
and specificity attainable. In order to achieve these objectives,
the QA/QC program developed by EPA consisted of the following
components (additional detailed documentation may be found in the
previously mentioned GCA Corporation report Quality Assurance
Plan, Love Canal Study, LC-1-619-206, available from NTIS).
First, internal QC programs were specified by EPA for use at
each of the analytical subcontractor laboratories. The QC pro-
grams required by EPA established minimally acceptable standards
that all subcontractors satisfied. Many subcontractors adopted
more stringent QC programs that were approved by EPA.
40
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Second, the prime contractor (GCA Corporation) managed the
day-to-day quality assurance program, which provided continuing
and immediate oversight of all subcontractors, and timely identi-
fication and correction of sampling and analytical problems (de-
tails regarding the results of this program may be found in Love
CanalMonitoring Program, GCA QA/QC Summary Report). The QA pro-
gram that the GCA Corporation managed was devised by EPA and
included the following components:
1. Requirements for sample collection, preservation, and
holding times
2. Requirements for on-site sampling systems audits and per-
sonnel performance audits
3. Requirements for analytical methods, calibrations, and
control chart usage
4. Requirements for external analytical QA programs, includ-
ing the use of EPA performance evaluation and quality con-
trol samples
5. Requirements for internal analytical QA programs, includ-
ing the measurement of reference compounds, method blanks,
laboratory control standards, laboratory duplicates, and
surrogates or target compound spikes. Requirements for
spiking concentrations, laboratory control standards, and
control limits were stipulated for some methods.
6. Requirements for the collection and analysis of a speci-
fied number of replicate field samples and field blanks
7. Requirements for splitting field samples between laborato-
ries
8. Precision and accuracy goals were specified as appropri-
ate .
Third, EPA performed an intentionally redundant retrospective
evaluation of the QA/QC program, which involved reviewing all of
the analytical data generated by the subcontractors, and validat-
ing those portions of the monitoring data satisfying EPA stan-
dards (details of this process are presented in Appendixes C
through E of this Volume). Briefly, the process of validating
data involved the purposeful rejection of certain analytical re-
sults whenever compelling QA/QC evidence was present that identi-
fied the occurrence of errors in sampling, preservation, or ana-
lytical method execution which were associated with those re-
sults. No other data (such as statistical "outliers") were elim-
inated from the Love Canal data base. Volume II contains a list-
ing of all validated Love Canal data.
41
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Finally, because many of the analytical methods employed for
medium-specific organic analyses were state-of-the-art procedures
not yet formally (multilaboratory) tested, the comprehensive
QA/QC procedures employed were designed to permit, as appropri-
ate, estimation of the precision and accuracy of these methods by
EPA. The basis for such estimation was through the acquisition
and analysis of QA specific duplicate and triplicate field sam-
ples at Love Canal, and the analysis of well-characterized ex-
ternal QC samples (that is, specially prepared samples whose ana-
lytes and concentration levels were unknown to the analytical
subcontractors) and internal QC samples. Procedures employed for
these purposes are described in the GCA Corporation document
Quality Assurance Plan, Love Canal Study, LC-1-619-206.
As used here, the term "accuracy" includes both qualitative
accuracy, the ability of a measuring system to correctly identify
the presence or absence of a particular analyte in a sample when
the analyte is actually present or absent, and quantitative ac-
curacy, the ability of a measuring system to specify the amount
of an analyte present in a particular sample. The term "preci-
sion" refers to the amount of variability (that is, the likely
range of values that would be observed in identically repeated
measurements) associated with any one particular measurement
value.
In order to determine the presence and concentration levels
of the relatively large number of targeted substances (presented
in Tables A-l and A-2 of Appendix A) to be determined in Love
Canal samples, an extensive, detailed set of procedures (proto-
cols) were established that stipulated the exact mariner in which
all sampling and analytical activities were to be conducted. Even
though the protocols used served to standardize all such activi-
ties, it must be recognized that the numerous complex actions re-
quired, and the sophisticated instrumentation employed, resulted
in a certain amount of unavoidable variability in the application
of measurement system methodologies. Knowledge about the vari-
ability inherent in all environmental measurement systems becomes
increasingly important as the concentration of the analyte(s) of
interest in a sample decreases. Consequently, for low-level
(sometimes called "trace") environmental measurements, it is es-
sential that the variability of the measurement systems used be
known (or be estimated), in order to understand the confidence
that can be associated with any one particular measurement value.
The establishment of appropriate QA/QC procedures was designed to
document fully the process by which the Love Canal monitoring
data were generated, and to provide some indication of measure-
ment systems variability. The reader interested in additional
detailed information on the QA/QC programs used at Love Canal,
and the results of these efforts, should consult Appendixes C
through E of this Volume, and the previously mentioned GCA Cor-
poration reports available from NTIS.
42
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Before concluding this section, it should be pointed out that
a comprehensive QA/QC effort was conducted by EPA at Love Canal.
As a result, the Love Canal data are carefully validated environ-
mental measurements, and (given the constraints previously men-
tioned) are representative of the current state-of-the-art in
environmental measurement methodology in terms of precision, ac-
curacy, and specificity.
3.3.1 Limits of Detection and Quantitation
The measurement of low-level ("trace") amounts of organic
compounds in environmental samples is a challenging task for the
analytical chemist. Because of the inherent uncertainties asso-
ciated with such efforts, it has become common practice to re-
quire that a certain concentration level of a compound be present
in a sample before an analyst will assert that the compound is
actually present. The smallest amount of a compound recognized
as measurable in a sample (with a given finite probability) is
called the limit of detection (LOD). The LOD varies from one
compound to another, from one sample matrix to another, from one
measurement system to another, and can vary in the same measure-
ment system from one determination to the next.
A concentration level somewhat higher than the LOD should be
established whenever applicable as the level at which the con-
centration of a compound present in a sample (with a given finite
probability) will be quantified. This concentration level of a
compound in a sample is referred to as the limit of quantitation
(LOQ). Concentration levels of compounds in the interval LOD to
LOQ are often, by convention, called "trace" values of the
compounds. The LOQ also varies from one compound to another,
from one sample matrix to another, from one measurement system to
another, and can vary on the same measurement system from one
determination to the next. Statistical analyses of the moni-
toring data generated from Love Canal field samples treated all
"trace" concentrations of compounds as positive occurrences (that
is, detections) of those compounds in samples analyzed. Appen-
dixes C through E (in the sections entitled "Limits of Detec-
tion/Quantitation") contain additional details on LOD and LOQ,
and present tables indicating LOD values for certain monitored
substances.
3.3.2 Precision and Accuracy Goals
For the analysis of organic compounds in all media, a primary
goal of maximizing specificity (that is, maximizing the probabil-
ity of correct compound identification) was established at the
initiation of the study. The approach selected to achieve this
goal was through the application of chromatographic methods that
use a mass spectrometer (MS) detector. In these methods, the
mass spectrometer was required to be operated in the repetitive
scanning mode. Compound identification criteria were provided
43
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that employed both relative chromatographic retention time infor-
mation and mass spectra data. The only exceptions to this ap-
proach to qualitative accuracy involved determinations of 2,3,7,
8-tetrachlorodibenzo-p-dioxin (2,3,7,8-TCDD), and a few pesti-
cides at below parts per billion levels. For 2,3,7,8-TCDD deter-
minations, which were measured at concentrations as low as 10
parts per trillion, the highly specific approach of high resolu-
tion gas chromatography/high resolution mass spectrometry (HRGC/
HRMS) with selected ion monitoring was used. For certain pesti-
cides determinations, which were measured at various low parts
per trillion levels, gas chromatography with an electron capture
detector (GC/ECD) was used. In addition, confirmation of pesti-
cide identification by GC/MS was required, whenever concentra-
tions permitted, to minimize false-positive identifications.
The requirement for complete spectra acquisition to assure
high qualitative accuracy in compound identification placed a
major constraint on the precision of concentration measurements,
and on method detection and quantitation limit goals. For exam-
ple, it is known (P. Olynyk, W. L. Budde, and J. W. Eichelberger,
J. Chromatographic Science, 1981, 19, 377) that in water, the ac-
ceptable total method precisions expected for one of the methods
used are in the relative standard deviation (RSD) range of 2 to
13 percent, depending on the analyte. Precisions better than
this were neither required nor expected of the analytical subcon-
tractors. Precisions better than 50 percent RSD were expected in
water and air; precisions better than 100 percent were expected
in the other media. Furthermore, it is also known (J. A. Glaser,
D. L. Foerst, G. D. McKee, S. A. Quave, and W. L. Budde, Environ-
mental Science and Technology, 1981, 1426) that in water, the
minimum method quantitation limits expected for the methods used
are in the range of 1 to 10 micrograms per liter (parts per bil-
lion), depending on the analyte; minimum method quantitation
limits were estimated for other methods and are reported in Ap-
pendixes D and E. Quantitation limits below these values were
neither required nor expected of the analytical subcontractors,
except as noted previously for 2,3,7,8-TCDD and certain pesti-
cides .
For metals analytes, highly reliable methods based on ab-
sorption and emission spectrometries were selected to assure high
qualitative accuracy in element identification. Precision and
method quantitation goals were of the same order of magnitude as
those described for the organic analytes.
The precision and accuracy of the monitoring data obtained
from Love Canal are documented in Appendixes C through E, in the
sections entitled "Estimates of Data Precision" and "Estimates of
Data Accuracy."
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3.4 DATA ANALYSIS AND DATA REPORTING
The entire EPA Love Canal validated data base is listed in
Volume II of this report. The data are organized by sampling area
and within each sampling area by sampling station (site). Within
each sampling site, the data are further organized according to a
medium/source/location taxonomy that facilitates reference to
particular collections of data. (See Table 2). For each analysis
reported, a wide variety of information is presented, including:
sample identification number; medium (for example, air); source
(for example, TENAX, PFOAM, or HIVOL); location (for example, LI
or L2 for living area, BA for basement, or Ol for outside); date
on which the sample was collected; time of day the sample was
collected; subcontractor responsible for sample collection; and
analysis information including analysis method, analysis labora-
tory, sample size, substances detected, and the corresponding
concentration of the substance in the sample.
In Figure 7, a sample page from the validated data listing
contained in Volume II is presented. Due to confidentiality
agreements, sampling locations are identified in this report only
by unique sampling area and station codes. In subsequent figures,
the approximate location of medium-specific sites in the vicinity
of the Declaration and Canal Areas is indicated, along with the
corresponding sampling area and station code.
Statistical summaries of the validated data are collected in
Volume III of this report. For the sake of consistency in pre-
senting data, the summaries constructed involved aggregating the
data by both sampling area, and by Declaration Area (sampling
areas 1 through 10), Canal Area (sampling area 11), and Control
Area (sampling area 99). It is recognized that for certain
medium/source combinations, the aggregation of data by sampling
area is inappropriate (for example, bedrock aquifer ground-water
results cannot be interpreted according to the sampling area
schema). Nonetheless, the data for all medium/source/location
combinations (which are presented in Volume III), follow the or-
ganizational convention described.
The analytical results from QA/QC sites (that is, sites at
which duplicate and triplicate samples were collected), where ex-
plicit identification of the site specific field sample was not
stipulated, were subjected to random (equiprobable) selection
prior to statistical analyses of the data. These same data were
also used for the production of certain graphical summaries of
the data that are presented in later sections of this Volume. As
a result of this action, significant conceptual difficulties were
avoided in dealing with the multiple sets of analytical results
from QA/QC sites; namely, problems that are associated with the
alternative procedure of attempting to represent the site by com-
puting mean concentrations whenever below detection (B) or trace
45
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«*RAW DATA LISTING**
THIS REPORT IS BASED ON VALIDATED DATA ENTERED INTO THE SYSTEM THROUGH 06/17/81 01 003
*»* SITE DATA «**
SAMPLING APEA 01 STATION 003 COORDS 400410 E 1122490 N MAP OVERl
*** SAMPLE DATA *»*
SAMPLE-ID A102I2 MEDIUM AIR SOURCE PFOAM SAMPLE DATE 09/08/80 START TIME 0653 CONTRACTOR GEOI1E
LOG LI PUMP 4784 START/END/AVG FLOW 1339.90/1297.30/1268.60 END TIME 2053 OUR 0720 VOL 913.39
*** ANALYSIS RESULTS ***
METHOD ECGCF SPECIFIC METHOD ANALYSIS LAB SWRI OU4N SIZE 0.0 N/A
COMPOUND CAS PC COHCEHTRATION REPORTED CONC COMMENT
POLYURETH.5NE PLUGS BELOU DETECTION LIMIT
*********** *********
»** SAMPLE DATA ***
SAMPLE-ID A10429 MEDIUM AIR SOUPCE PFOAM SAMPLE DATE 09/16/80 START TIME 0843 CONTRftCTOR GEOME
LOC LI FUMP 4764 START/EUO/AVG FLOW 1205.00/1347.00/1276.00 END TIME 2043 PUR 0720 VOL 918.72
*** ANALYSIS RESULTS ***
METHOD ECGCF SPECIFIC METHOD ANALYSIS LAB GSLA QUAN SIZE 0.0 N/A
COMPOUND CAS PC CONCENTRATION REPORTED CONC COMMENT
POLYURETHANE PLUGS BELOW DETECTION LIMIT
*** SAMPLE DATA ***
SAMPLE-ID A10616 MEDIUM AIR SOURCE PF04M SAMPLE DATE 09/21/80 START TIME 0831 CONTRACTOR GEOME
LCC LI PUMP 5940 START/END/AVG FLCW 1272.40/1267.00/1269.70 END TIME 2031 OUR 0720 VOL 914.18
*** ANALYSIS RESULTS ***
METHOD ECGCF SPECIFIC METHOD ANALYSIS LAB GSLA QUAN SIZE 0.0 N/A
COMPOUND CAS PC CONCENTRATION REPORTED CONC COMMENT
POLYURETHANE PLUGS BELOW DETECTION LIMIT
*** SAMPLE DATA *'*
SAMPLE-ID A10298 MEDIUM AIR SOURCE TENAX SAMPLE DATE 09/08/80 START TIME 0853 CONTRACTOR SEOME
LOC LI PUMP 10616 START/END/AVG FLOW eS.al/ 30.69/ 29.45 END TIME 2053 DUR 0720 VOL 21.20
*** ANALYSIS RESULTS ***
METHOD GCMST SPECIFIC METHOD ANALYSIS LAB BCL QUAN SIZE 0.0 N/A
COMPOUND CAS PC CONCENTRATION REPORTED CONC COMMENT
BENZENE 71-43-2 T01 3.679 UG/M3 78.000 NG/SM EXTRAPOLATED
0-DICHLCROBENZENE °5-SO-l T07 49.009 UG/MJ 1039.000 HS/S11 EXTRAPOLATED
1,1,2,2-TETRACHLOPOETHYLENE 127-18-4 T09 5.1S8 UG/M3 110.000 NG/SM EXTRAPOLATED
TOLUENE 108-88-3 T10 41.745 UG/M3 885.000 N3/SM EXTRAPOLATED
DICHLCPOMETHANE 75- 9-2 T23 QU4LITATIVE
PHENOL 108-95-2 T24 QUALITATIVE
0-XYLENE 95-47-6 T25 QUALITATIVE
M-XYLEHE 108-38-3 T26 QUALITATIVE
P-XYLENE 106-42-3 T27 QUALITATIVE
*** SAMPLE DATA ***
SAMPLE-ID A10485 MEDIUM AIR SOURCE TENAX SAMPLE DATE 09/16/80 START TIME 0844 CONTRACTOR GEOME
LOC LI PUMP 10616 START/END/AVG FLCW 30.60/ 30.40/ 30.50 END TIME 2044 DU3 0720 VOL 21.96
*** ANALYSIS RESULTS »**
METHOD GCMST SPECIFIC METHOD ANALYSIS LAB PEDC QUAN SIZE 0.0 N/A
COMPOUND CAS PC CONCENTRATION REPORTED CONC COMMENT
Figure 7. Sample Page of the Data Listing Presented in
Volume II.
46
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(T) values were obtained. However, the procedure followed re-
quires that care must be exercised when attempting to compare
Volume II results with Volume III summary tables.
The only statistical tests performed on the Love Canal moni-
toring data involved substance-by-substance comparisons between
Declaration Area, Canal Area, and Control Area aggregations of
the data. Differences in the extent of environmental contamina-
tion in areas of interest were assessed statistically by a dif-
ference of percentages test, using Fisher's exact test to deter-
mine probability values. The extent of contamination in an area
was defined as the percent of positive determinations (qualita-
tive identifications) of the substance of interest at a trace or
greater concentration level. Differences in the degree of envi-
ronmental contamination in areas of interest were assessed sta-
tistically through the use of a difference in medians test, again
using Fisher's exact test for the computation of probability
values. Due to the large number of substances monitored, and the
large number of substance-by-substance comparisons that can be
made, statistical inference problems may occur. The reader is
cautioned to realize that for a given level of significance a, a
proportion of results approximately equal to a will, by chance,
demonstrate statistical significance. Such outcomes, known as
Type I errors (that is, rejecting the null hypothesis when it is
true), must be considered when attempting to evaluate the statis-
tical results presented in Volume III.
The statistical criteria established for assessing the extent
and degree of environmental contamination in an area of interest
were as follows. First, directional alternative hypotheses were
postulated, incorporating the expectation of greater contamina-
tion in the Canal Area than in the Declaration Area, and greater
contamination in the Declaration Area than in the Control Area
(control sites are identified for selected medium/source/location
combinations in Appendix B, Table 8-1). And second, a level of
significance of <*= 0.10 was selected (as compared to the more
commonly employed levels of 0.05 or 0.01) for rejection of the
null hypothesis of no difference in environmental contamination
between the areas monitored. This level of significance was
selected to obtain acceptably high power in the statistical test
procedures employed, particularly when comparing the Declaration
Area monitoring data to the Control Area monitoring data for
certain medium/source/location combinations. As a result of
these two actions, the probability of detecting statistical
trends in the monitoring data that were suggestive of the migra-
tion of contaminants from Love Canal into the Declaration Area
was increased considerably above the usual practice.
3.5 LIMITATIONS
As was mentioned in Section 1.1.6, the EPA Love Canal study
was limited by both time and budgetary constraints. As a result,
47
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medium-specific sample designs and site-specific sampling frames
were employed, and a large number of field samples were collected
over a relatively short time interval. Obviously, therefore, the
1980 EPA Love Canal study represents but a finite characteriza-
tion of environmental conditions in the Love Canal Declaration
Area, and retrospective assessment of the extent and degree of
contamination present in the Declaration Area (for example, air
pollution levels) at some past date is uncertain, and has not
been performed.
48
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CHAPTER 4
RESULTS OF THE INVESTIGATIONS
The major results of the EPA Love Canal environmental moni-
toring program have been organized by environmental medium and
are presented in subsequent subsections of this report. The or-
ganization of this section on results deliberately follows the
same sequence of topics that was presented in Section 1.2 of the
Overview. The intent here is to provide the reader with addi-
tional details on sampling, analytical, and interpretive aspects
of the Love Canal monitoring program.
4.1 HYDROGEOLOGIC PROGRAM
The hydrogeological study conducted by EPA at Love Canal was
multidimensional. Integral parts included defining the geology
and occurrence of ground water within the study area, locating
areas of ground-water contamination (both vertically and later-
ally) , and determining the directions and rates of movement of
contaminants through the subsurface soils and rock.
The first phase of the program involved the collection and
analysis of existing geological and hydrological data in order to
guide the project through subsequent stages. Included in this
phase, and occurring concurrently, were geophysical investiga-
tions using the most advanced techniques in ground-penetrating
radar and electromagnetic conductivity. These activities were
designed to determine the occurrence of ground water in the study
area, to help locate potential plumes of contamination moving
from the former canal, and to provide a partial basis for select-
ing monitoring well site locations.
The second phase of the program involved a test drilling
program that was initially designed to determine the number and
depth of permeable water-bearing zones existing vertically in
both the overburden and underlying bedrock, and to determine if
ground water in the overburden and bedrock were connected or if
separate aquifers existed. Data developed during the test drill-
ing program served to guide the subsequent installation of moni-
toring wells. The 174 monitoring wells installed by EPA at Love
49
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Canal were used for the purpose of obtaining samples of the sub-
surface materials at selected drilling sites, obtaining water-
level data, determining aquifer flow characteristics, and col-
lecting a large number of samples of ground water for chemical
analysis. Stringent requirements were imposed on all aspects of
well construction in order to avoid potential cross-contamination
of water-bearing zones. Substances of interest that were rou-
tinely determined in ground-water samples are identified in Ap-
pendix A of this Volume.
The third phase of the hydrogeologic program was the devel-
opment of a verified ground-water model for predicting the move-
ment of contaminants in the ground water under varying conditions
of recharge and discharge. An extensive report on the results of
this effort, Final Report on Ground-WaterFlow Modeling Study of
theLove Canal, New York, is available from NTIS.
Figures 8 and 9 identify the locations of wells drilled in
the general Love Canal area as part of the EPA hydrogeologic
program. Figure 8 identifies the location of monitoring wells in
the vicinity of Love Canal that were drilled into the overburden
and used to monitor contamination in the shallow system; these
wells were referred to as "A Wells." In Figure 9, the location
of monitoring wells in the vicinity of Love Canal that were
drilled into the underlying bedrock, and used for monitoring
contamination in the bedrock aquifer, are indicated? these wells
were referred to as "B Wells."
4.1.1 Geology of the Love Canal Area
In order to understand the potential for contamination migra-
ting from the former canal, a thorough understanding of the geo-
logy, as well as the occurrence and movement of ground water, at
the site was necessary. The information obtained from the geo-
logical^ portion of the program was used to optimize the placement
of ground-water monitoring wells and was also used partially to
guide the selection of soil sampling locations.
4.1.1.1 Geological Setting
During the Pleistocene epoch, western New York State experi-
enced several periods of glaciation. As a result, the general
Love Canal area exhibits features that are characteristic of gla-
cial erosion and deposition. Bedrock in the vicinity of Love Ca-
nal consists of a unit known as Lockport Dolomite, a mineral de-
posit composed of calcium magnesium carbonate. Underlying the
Lockport Dolomite is a relatively impermeable unit referred to as
Rochester Shale. The Lockport Dolomite was encountered during
well drilling activities at a depth of approximately 20 to 45
feet below the land surface, and ranged in thickness from approx-
imately 160 to 180 feet. Generally, the Lockport Dolomite may be
50
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x99015
x99016
x98072
\03517x !
03B11 xxxiio41 H035x
03525
x 05030
99550x
x 07015
x 07014
x07019
X07504
x07501
x09019
x 09015
x11041
Figure 8. Well A (Overburden) Installation Site Codes.
51
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X99015
x99016
x05027
X07015
X07014
X07019
X99072
x05030
99550x
I
X07504
X07051
X10041
x 10051
x10040
X99560
Figure 9. Well B (Bedrock) Installation Site Codes,
52
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described as a dark gray to brown, massive to thin-bedded dolo-
mite, locally containing small, irregularly shaped masses of gyp-
sum and calcite. The Lockport Dolomite was found to dip towards
the south at a rate of approximately 30 feet per mile.
In the general Love Canal area, the Lockport Dolomite is
overlaid by a deposit of glacial till ranging in thickness from
approximately 1 to 5 feet; in the Canal Area the till was found
to vary from approximately 5 to 20 feet thick. The glacial till
consists of an unsorted mixture of clay, sand, and rocks that was
deposited on the Lockport Dolomite by the advance and retreat of
glaciers. Prom field testing activities the glacial till was
found to be relatively impermeable (K of approximately 10 '
cm/s).
Layers of clay, silt, and fine sand exist above the glacial
till and were found to vary in thickness from approximately 6 to
29 feet. These materials were deposited in the area by lakes
that were formed by the melting and retreat of glaciers during
the late Quaternary period. Two glacial lakes were chiefly re-
sponsible for these deposits. The older glacial lake, Lake Dana,
deposited reddish sediments, which had eroded from bedrock to the
north, on top of the till. The lacustrine deposits attributable
to Lake Dana were found to vary from approximately 2 to 20 feet
thick, and were characterized as very moist to wet, very plastic,
very sticky, silty-clay to clay. The permeability of these mates
rials was found to be relatively low (K of approximately 10~
cm/s).
Above the Lake Dana deposits were the deposits of Lake Tona-
wanda, which ranged in thickness from approximately 3 to 8 feet.
The materials deposited by Lake Tonawanda tended to be coarser,
reddish brown to gray sediments that were characterized as some-
what moist, firm, varved, silty-clay to clay. At a depth of ap-
proximately 5 to 8 feet below surface levels the lacustrine de-
posits were found to be extremely firm to very firm silty-clay,
and vertical dessication cracks have sometimes been noted as pre-
sent (according to reports prepared by other investigators). The
permeability of the Lake Tonawanda deposits was found to be gen-
erally low (K of approximately 10 'cm/s).
Above the Lake Tonawanda deposits were layers of silty sand,
clayey silt, and other fill materials varying in thickness from
but a few inches to approximately 3 feet in the general Love Ca-
nal area. The permeability of these materials was found to be
greater than the underlying clays (K greater than or equal to ap-
proximately 10 cm/s). Also present in the lacustrine sediments
were random deposits of more sandy materials occurring in the
form of sand lenses. These more permeable sandy zones were found
to occur neither in considerable thickness nor to extend over
large areas. Rather, these features were found to occur as
53
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typically small, generally disconnected deposits as is character-
istic of heterogeneous lacustrine material. Figure 10 summarizes
in general terms the geologic units found in the Love Canal area.
4.1.1.2 Topography and Drainage
The Love Canal site is located on the flood plain of the Nia-
gara River within the eastern limit of the City of Niagara Falls,
New York. The eastern border of the Declaration Area adjoins,
and is partially located in, the Town of Wheatfield, New York.
The general area (Figure 11) is relatively flat and is dominated
by three major features: the United States and Canadian Falls;
the Niagara gorge; and the Niagara Escarpment.
The Niagara Escarpment, a steep cliff marking the end of high
land, extends in an easterly direction from the Niagara River im-
mediately south of Lewiston, New York to well beyond the general
Love Canal area. At the Niagara River, the escarpment is approx-
imately 200 feet high, and gradually diminishes towcird the east
into a broad, gently-sloping incline. North of the escarpment the
land slopes gently towards Lake Ontario. South of the escarpment
the land slopes gently toward the upper Niagara River.
Streams in the general Love Canal area eventually flow into
the Niagara River. On the north, Bergholtz Creek and Black Creek
(which joins Bergholtz Creek near 96th Street) flow in an east-
to-west direction. Bergholtz Creek joins Cayuga Creek at a point
northwest of the former canal near the intersection of Cayuga
Drive and 88th Street. Cayuga Creek flows in a generally north
to south direction and empties into the Little Niagara River near
South 87th Street. The Little Niagara River joins the Niagara
River on the west side of Cayuga Island. Given the existence of
certain climate- and weather-related conditions and the gentle
slopes of the three creekbeds, local and temporary reversals of
water flow direction are known to occur in Cayuga, Bergholtz, and
Black Creeks.
Prior to the early 1970's, a number of surface soil features,
sometimes referred to as swales, existed in the general Love
Canal area. Swales were generally shallow depressions (less than
10 feet deep) that presumably served to preferentially drain the
area of surface water run-off. The location of known former
swales in the general Love Canal area are depicted in Figure 2 by
superimposed wavy lines. The identification of former swales
throughout the area was performed by the Remote Sensing Program,
School of Civil and Environmental Engineering, Cornell
University, from the inspection of historical aerial photographs
of the site taken between 1938 and 1966.
A variety of arguments have been offered concerning the po-
tential importance of swales in contributing to the migration of
contaminants from Love Canal to the adjacent residential areas.
54
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Ol
Ul
«~r- - <»•. -•-•. «'fc»>"~.., •
/ / / / ~ / /
/ / / / / / /
±
/ / / / /
j_ /.__./....: / / /
/ J / /.J
,l-Q , I ...- I X
J 71. I I
— / — /—/ —/ — -
=>—?--J-jr-,cr j~_a_-
System
Quaternary
Silurian
3
Middle
4!
0
Formation
Unit
Pill
Lacustrine
Deposits
Glacial
Till
Lockport
Dolomite
Rochester
Shale
Thickness
(Feet)
0.1-3
6-29
1-25
160-180
SO
General Geologic and Hydrologic Characteristics
- Covers nearly entire study area
- Varies from local soil material to construction rubble and
industrial wastes
- Sand lenses randomly occur as elongated lacustrine deposits
throughout region and consist of loamy to sandy clay; some-
times exposed at. surface in undisturbed areas
- Total thickness of former glacial lake deposits increases
from north to south in vicinity of canal
- Upper sequence deposited in former Lake Tonawanda (3-8 feet
thick) is reddish brown to gray, moist, firm to very firm,
varved, silty-clay to clay; dessication cracks reported in
selective areas within sequence
- Lower sequence (2-20 feet thick) attributable to former Lake
Dana is reddish brown, very moist to wet, very plastic , very
sticky, silty-clay to clay
- Permeability of lacustrine deposits is generally low
- Reddish brown, moist, firm, silty to sandy clay with gravel
and cobbles j sandy zones t well-sorted gravel
- Two or three ridges of till oriented NE-SW are in Canal Area
- General ly low permeabi 11 t,y
- Approximately 5-20 feet thick in Canal Area
- Dark gray to brown, massive to thin bedded dolomite dipping
at low angle to south? secondary deposits of sul fides ,
su 1 fates , and carbonates occur throughout the format ion
- Principal aquifer in Niagara Falls area; major producing
zones in upper part of formation
- Artesian and unconfined water table conditions exist associ-
ated with vertical fracture zones, cavities formed by solu-
tion of minerals and between bedding planas
- Vertical joint system hydraulically connected to Niagara
River
- Dark -gray calcareous shale? relatively impermeable
NOT TO SCALE
Figure 10. Generalized Columnar Section of Geologic Units in Love Canal Area,
-------
HURON PLAIN I
,. J
SCALE
CBZ
10
BL-BL
10
20
30
40
MILES
Figure 11.
Index Map Showing Location of Project Area and
Physiographic Provinces.
56
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For example, it has been argued by some that if the former swales
were filled with rubble and more permeable soils during periods
of residential construction activity near Love Canal, then they
may have preferentially allowed chemicals to migrate some dis-
tance from the dump site into the surrounding neighborhood, par-
ticularly in response to certain climate influenced ground-water
conditions (the so-called "overflowing bathtub" analogy frequent-
ly used to describe unusually high ground-water conditions at the
site during the period 1976 to 1978). Alternatively, it has been
offered that when the landfill was open, water impounded in the
canal was contaminated by dumping activities and displaced from
the canal into the still open intersecting swales, and subse-
quently into the surrounding neighborhood. Finally, it has been
argued that if the swales had been filled with already contami-
nated soils that were removed from the Love Canal site after
dumping activities were concluded in 1953 (the so-called "trans-
port by dump truck" conjecture}, then the surrounding neighbor-
hood would exhibit isolated areas of relatively low-level con-
tamination in some of the former swales and other low-lying
areas.
As a result of the generally level topography of the site,
surface water run-off was historically poor. During rainy per-
iods, areas of ponded water and marshy ground formed, typically
to the southwest and southeast of the canal. Houses that were
later built in areas where water problems historically occurred
have been referred to by other investigators as "wet" houses; for
example, a wet/dry dichotomy of Love Canal houses was developed
and used for classification purposes by NYS DOH in their epidemi-
ological investigations at Love Canal. The NYS DOH wet/dry class-
ification scheme was also used by EPA for the selection of a num-
ber of sampling sites.
At the present time, surface-water drainage principally oc-
curs in the general Love Canal area through a system of storm
sewers installed by the City of Niagara Falls. Typically, storm
sewers in the Love Canal Declaration Area were found to be ap-
proximately 10 feet deep.
Of particular interest to this investigation were the storm
sewer lines that virtually surround the Canal Area, On 97th
Street a storm sewer line starts at approximately Read Avenue,
heads northward, and eventually discharges into Black Creek near
96th Street. A storm sewer lateral on Read Avenue, terminating
in a catch basin located approximately midpoint between 97th and
99th Streets, was built by the city in 1960. Prior to remedial
construction, the lateral on Read Avenue was connected to the
97th Street northward flow storm sewer line. On Colvin Boulevard
a storm sewer line originating near 98th Street heads westward
and joins the 97th Street storm sewer. In addition, prior to re-
medial construction a catch basin installed for drainage purposes
by the City of Niagara Falls near the former canal boundary,
57
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along the property line at 949-953 97tin Street, was connected to
the 97th Street northward flowing storm sewer line. Figure 12
shows the approximate location of the features just mentioned and
other relevant Canal Area storm sewers.
The southward flowing storm sewer line on 97th Street origi-
nates near Read Avenue and connects to a storm sewer line on
Frontier Avenue that flows eastward, and eventually discharges
into the Niagara River at the so-called 102nd Street outfall.
Prior to remedial construction, a storm sewer lateral on Wheat-
field Avenue, terminating in a catch basin located approximately
170 feet east of 97th Street, was connected to the 97th Street
southward flowing storm sewer line.
On 99th Street the northward flowing storm sewer line origi-
nates near Read Avenue and eventually discharges into Black Creek
(which is located in a below-grade culvert from 98th Street to
approximately the imaginary northward extension of 102nd Street),
between 101st and 102nd Streets. The southward-flow 99th Street
storm sewer consists of a portion between Read and Wheatfield
Avenues, and another portion originating near Wheatfield Avenue.
The portion of the 99th Street storm sewer line between Read and
Wheatfield Avenues flows south and turns eastward on Wheatfield
Avenue, turns south again on 101st Street, and eventually dis-
charges into the Niagara River at the 102nd Street outfall. Prior
to remedial construction, the French drain built around the 99th
Street Elementary School was connected to the 99th Street storm
sewer line just north of Wheatfield Avenue. (See Figure 12). In
addition, prior to remedial construction, a storm sewer lateral
on Wheatfield Avenue, terminating in a catch basin located ap-
proximately 170 feet west of 99th Street, was connected to the
99th Street storm sewer line at Wheatfield Avenue. The portion
of the 99th Street storm sewer line originating south of Wheat-
field Avenue is connected to the Frontier Avenue storm sewer line
and eventually discharges into the Niagara River at the 102nd
Street outfall.
According to NYS DEC field inspection notes and NYS DOH re-
ports, the storm sewer lines installed by the City of Niagara
Falls around Love Canal were built without granular bedding and
the trenches were backfilled with the excavated natural soils.
As a result of this construction practice, a "curtain of clay"
around the site, likely severing all naturally occurring more
permeable soil pathways leading from the former canal (including
filled former swales), may have been built inadvertently by the
city. The storm sewer line currently under Frontier Avenue,
which was relocated by NYS DOT in 1968, does have a granular bed-
ding, but it was encompassed by the barrier drain system con-
structed by NYS DEC. The storm sewer leads and catch basins on
Read and Wheatfield Avenues were all removed during remedial con-
struction, as was the catch basin and pipe located near the for-
mer canal on 97th Street, and the entire French drain system
58
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Ul
VO
A FLOW DIRECTION
• MANHOLE
• BACKYARD CATCH BASIN
(REMOVED)
DEURO DR.
Figure 12. Location of Storm Sewers Near Love Canal.
-------
around the 99th Street Elementary School. Across Wheatfield
Avenue, a natural gas main, as well as a sanitary sewer line in-
stalled by the City of Niagara Falls in 1957, still remain. Ac-
cording to NYS DEC field inspection notes, neither line was con-
structed with a granular bedding and both were intercepted by the
barrier drain system installed by NYS DEC. In 1980 the City of
Niagara Falls plugged the Wheatfield Avenue sanitary sewer line
near the intersection of Wheatfield Avenue and 99th Street.
As a result of the relatively close proximity of storm sewer
lines to Love Canal, interest was focused on characterizing their
current transport of contaminants to area creeks and rivers. It
was recognized that prior to remedial construction, a number of
sources may have contributed to storm sewer contamination includ-
ing: (1) overland flow of contaminants that were likely captured
by curb drains near ring 1 houses; (2) subsurface migration and
infiltration of contaminants into the storm sewers, particularly
through the storm sewer laterals on Read and Wheatfield Avenues,
the catch basin and pipe located near the former canal at 949-953
97th Street and connected to the 97th Street northward-flow storm
sewer line, and the French drain built around the 99th Street
Elementary School; and (3) the discharge of potentially contami-
nated water and sediment taken-up by basement sump pumps in ring
1 and ring 2 houses and discharged into Canal Area storm sewers.
As a result of remedial construction activities and the evacua-
tion of ring 1 and ring 2 families by 1979, the only potentially
remaining source of continuing storm sewer contamination was
through the residual subsurface migration and infiltration of
contaminants into storm sewer lines on 97th and 99th Streets,
Colvin Boulevard, and Frontier Avenue.
4.1.1.3 Occurrence of Ground Water
Ground water was found to occur in the Lockport Dolomite in
three types of openings: (1) bedding planes—horizontal planes
that separate individual layers of the rock; (2) vertical
joints—fractures that interrupt the horizontal continuity of the
rock unit; and (3) solution cavities—cavities in the rock from
which gypsum and calcite have been dissolved. Most of the water
moving through the upper portion of the Lockport Dolomite was
found to move through the horizontal bedding planes contained in
the top 10 to 16 feet of the unit. Ground-water flow in the up-
per portion of the Lockport (the top 20 feet of the unit), was
found to be affected by the major trends of vertical fractures
connecting the bedding planes. The lower portion of the Lockport
(145 to 170 feet thick) was characterized by seven distinct
water-bearing zones having well-developed bedding plane separa-
tions. Flow in the lower portion of the Lockport Dolomite was
found to generally follow the inclination of the formation.
Field tests conducted on the bedrock aquifer yielded the fol-
lowing results: (1) the Lockport Dolomite is not a homogeneous
aquifer, but contains distinct water-bearing zones; (2) the upper
portion of the rock has significant vertical permeability; (3)
60
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the primary water-bearing zones are in the upper part of the
aquifer; (4) fractures have a substantial effect on the rate and
direction of ground-water movement in the upper portion of the
bedrock? (5) the upper portion of the bedrock aquifer is hydrau-
lically connected to the Niagara River; and (6) the bedrock aqui-
fer in the vicinity of Love Canal is confined below by the Roch-
ester Shale and above by the glacial till, and is artesian.
The deposits above the Lockport Dolomite (the overburden
material) were found not to be significant sources of water for
the area. The unconfined water-table aquifer existing in the
overburden material was found to be bounded by Bergholtz and
Black Creeks on the north, Cayuga Creek on the west, and the
Little Niagara and Niagara Rivers on the south. In general, the
glacial till and the two silty-clay units were found to be of low
permeability with small areas of sandy layers occurring within
where ground water could move more readily.
4.1.2 Geophysical Investigations
The geophysical investigations conducted at Love Canal were
performed using an integrated approach employing multiple surface
remote-sensing techniques. This approach was adopted in order to
permit the correlation of data records obtained from two or more
remote sensing techniques employed at a particular location. Due
to technical (that is, instrument) requirements, geophysical mea-
surements were conducted only in those areas around Love Canal
that were relatively free from residential interferences. The
techniques listed in Table 5 summarize the geophysical methods
employed at Love Canal, their mode of measurement, and the type
of information each technique provided.
4.1.2.1 Objectives of the Geophysical Investigations
The overall goal of the geophysical investigations performed
at Love Canal was to provide basic information concerning the hy-
drogeologic characteristics of the site. Specific objectives
were:
1. To furnish information concerning the natural hydrogeo-
logic variation of the site that could aid in understand-
ing the ground-water transport of contaminants from the
former canal.
2. To investigate the former canal and Canal Area using geo-
physical methods in order to tentatively identify and as-
sess the potential for migration of contaminants from the
site.
3. To provide data that would aid in the placement of some
monitoring wells used to obtain information on ground-
water contamination.
61
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TABLE 5. GEOPHYSICAL METHODS AND APPLICATIONS
Method
Ground
Penetrating
Radar
Responds to
Changes in:
Complex
dielectric
constant
Mode of
Measurement
Continuous
Application to
Love Canal Setting
--Provides continuous soil
profiles to 3-6 feet
— Reveals changes in soil
stratigraphy and drainage
patterns, and discerns
areas of fill
Electromagnetics
• Shallow EM
Bulk
electrical
conductivity
Continuous
and station
measurements
Deep EM
Bulk
electrical
conductivity
Continuous
and station
measurements
Resistivity
Sounding
Seismic
• Reflection
• Refraction
Bulk
electrical
resistivity
Station
measurements
Soil or rock
"velocity"
contrasts
Soil or rock
"velocity"
contrasts
Station
measurements
Station
measurements
Metal
Detector
Magnetometer
Electrical
conductivity
Magnetic
Continuous
Continuous
-Provides continuous spa-
tial or station measure-
ments of bulk conductivi-
ty to depths of approxi-
mately 18 feet
-Reveals spatial changes
in geo/hydrologic condi-
tions and areas of con-
ductive contamination
-Provides continuous spa-
tial or station measure-
ments of bulk conductivi-
ty to depths of 45-50
feet
-Shows spatial changes in
geo/hydrologic conditions
and discriminates areas
of conductive contamina-
tion
-Provides data on changes
in resistivity with depth
-Enables detailed assess-
ment of selected anoma-
lies delineated in EM
data
-Provides data on subsur-
face stratification
-Provides data on subsur-
face stratification,
thickness, and depth of
layers
-Provides a measurement of
the "velocity" or density
of the soil or lithified
components
-Provides a means of map-
ping location and esti-
mating quantity of buried
metals (e.g., barrels) to
a maximum depth of 5-10
feet for single targets
-Provides a means of
mapping locations and
estimating quantity of
buried ferrous metals at
depths up to 10-18 feet
for single targets
62
-------
4. To identify subsurface anomalies (which may include such
features as swales and sand lenses) that may serve as
preferential transport pathways for the migration of
contaminants.
4.1.2.2 Major Results of the Geophysical Investigations
The multiple remote sensing geophysical methods used at Love
Canal provided information on the geological variability of the
general Love Canal area, and yielded suggestive information con-
cerning the detection and delineation of potential migration
pathways from the former canal. Figure 13 illustrates the type
of information obtained from one of the remote sensing (shallow
electromagnetic) geophysical methods used? the figure depicts the
likely presence of contaminants located directly in and immedi-
ately adjacent to the landfill. A graphical summary of the in-
ferred findings from the geophysical investigations conducted at
Love Canal is presented in Figure 14. More detailed information
on the results of the geophysical investigations conducted at
Love Canal can be found in Geophys ica1 Investigat ion Re suits,
Love Canal, New York, available from NTIS.
4.1.3 Hydrology of the Love Canal Area
The hydrology of the general Love Canal area was determined
from a combination of activities that incorporated: (!) review-
ing the results of studies previously conducted in the region;
(2) the results obtained from EPA geophysical surveys of the gen-
eral Love Canal area; (3) the results obtained from EPA geolog-
ical surveys of the area conducted during the construction of
ground-water monitoring wells? and (4) the development and veri-
fication of a ground-water movement model of the area.
As part of the hydrogeologic program, a total of 174 ground-
water monitoring wells (A and B Wells) were installed throughout
the general area. During the investigation, five different types
of wells were constructed. Monitoring wells installed in the
overburden and screened in the silty clays above the glacial till
were referred to as A Wells. Shallow bedrock monitoring wells
were drilled 5 feet into the Lockport Dolomite and were referred
to as B Wells. C Wells were monitoring wells drilled through the
dolomite and into the underlying Rochester Shale. D Wells were
originally B Wells that were extended to greater depths in the
dolomite for hydrogeologic testing purposes. And T Wells were
wells that were screened at various levels in the overburden for
hydrogeologic testing purposes. The distribution of well types
constructed during the program was: 89 A Wells; 85 B Wells; 4 C
Wells; 3 B Wells were modified to D Wells; and 4 T Wells. A com-
plete description of the hydrogeologic program, including well
logs and as-built diagrams for all wells, can be found in the re-
port TheGround-Water Monitoring Program at Love Canal, available
from NTIS. Figures 15 and 16 illustrate the typical installation
of shallow overburden and bedrock wells at Love Canal.
63
-------
-------
LEGEND
HIGH, RELATIVE ELECTROMAGNETIC CONDUCTIVITY
LOW
MODERATELY HIGH CONDUCTIVITY
EXTREMELY HIGH CONDUCTIVITY
SUSPECTED SWALE
SUSPECTED SAND LENS
Figure 14. Site Map Showing Major Results of
Geophysical Survey.
65
-------
Hydrologic testing of the bedrock aquifer was conducted using
pumping tests to determine the transmissivity and storage coeffi-
cient of the aquifer. These values were determined empirically
to be 0.015 square feet per second and 1.49 x 10 respectively.
The following results were determined from the hydrologie testing
conducted at Love Canal.
1. The Lockport Dolomite is not a homogeneous aquifer, but
contains distinct water-bearing zones.
2. The upper portion of the unit has significant vertical
permeability.
3. The primary water-bearing zones are located in the upper
portion of the dolomite.
4. Fractures substantially affect both the rate and direction
of ground-water movement in the upper portion of the bed-
rock.
5. In the well locations tested, no hydraulic connection
apparently exists between the overburden and the bedrock.
4.1.3.1 Ground-Water Movement
The Lockport Dolomite aquifer maintains steady-state flow on
a regional basis by recharge from the topographic high occurring
near the Niagara Escarpment. Discharge generally occurs along
the Niagara Escarpment, along the gorge wall of the lower Niagara
River, towards the covered conduits of the Niagara Power Project,
and along parts of the upper Niagara River. In the general Love
Canal area, the gradient of ground-water movement in the dolomite
is south and southwesterly towards the upper Niagara River. On
the basis of bedrock aquifer tests conducted by EPA at Love Ca-
nal, it was estimated that if contaminants were to enter the
Lockport Dolomite at the southern end of Love Canal, and assuming
no attenuation, the average length of time required for the con-
taminants to reach the upper Niagara River would be approximately
1,000 days. In Figures 17 and 18 the potentiometric surface of
the Lockport Dolomite is presented from both a regional and local
perspective. The data used to construct Figure 17 were derived
from R. H. Johnston, Ground Water in the Niagara Falls Area, New
York, State of New York Conservation Department Water Resources
Commission Bulletin GW-53 (1964).
As was mentioned previously, the shallow ground-water system
in the general Love Canal area is probably bounded toward the
north by Bergholtz and Black Creeks, toward the west by Cayuga
Creek, and toward the south by the Little Niagara River and the
Niagara River. In Figure 19 the static water table of the over-
burden aquifer is presented. The elevations shown in Figure 19
indicate that during the study period, discontinuities likely
66
-------
LOCKING CAP ~
10" VAULT -
SET IN GROUT
GROUT
BENTONITE-
OVERBURDEN
SILICA SAND
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-------
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SET IN GROUT &£>
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^9 * * • ^'^^ *» / * ^ * /
y>* * • . GLACIAL
s "* " - TILL '-"'O
3\ x x
£ \ \
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' , , X. LOCKPORT X
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? \
4\ \ \
< \ \
/ \ \
t \ \
^ \ \ \
i-
^
^
^
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^
^
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LAND SURFACE
Figure 16. Completed Bedrock Well.
68
-------
cr>
vo
PUMPED-STORAGE
RESERVOIR NIAGARA
POWER PROJECT
AVERAGE ELEVATION
645 FEET
GENERALIZED STEADY-STATE
POTENTIOMETRIC SURFACE IN
LOCKPORT DOLOMITE (DATA
FROM JOHNSTON, 1964);
FEET ABOVE MEAN SEA LEVEL;
CONTOUR INTERVAL = 10 FEET
AMERICAN
FALLS
MAJOR
PUMPING
CENTER
DATA POINT LOCATIONS
SCALE
1 MILE
Figure 17. Regional Lockport Dolomite Potentiometric Surface.
-------
565.4
564.7
564.6
564.7
564.6
564.7
564.6
564.7 563.9
564.6
564,7
564.8
564.9
564.8
564.9
564.2 564.3.
564,2 ^
I 564.4
564.2
564.0
565.3
565.4
565.3
565.0
565.0
565.0
564.9
565.0
565.3
565.0
665.0
565 J
565.1
565.0
566.0
565.2
565.2
NOTE: VALUES REPORTED ARE IN FEET ABOVE MEAN SEA LEVEL.
THE CONTOUR INTERVAL USED IS 0.5 FOOT.
Figure 18. Lockport Dolomite Potentiometric Surface,
70
-------
existed in the shallow system. Due to the generally low perme-
ability of overburden materials and the relatively short period
of time for field measurement of water level elevations, the sur-
face presented should be interpreted with considerable caution.
Even though the surface may only approximate a steady-state at
one particular point in time, some general trends can be noted.
As may be seen in the illustration, the water surface elevations
suggest a general southwesterly gradient with a possible ground-
water mound near the north end of the landfill and a slight de-
pression near the south end of the landfill. As a result of a
broken water line on 97th Street (located near the intersection
of 96th Street with 97th Street between Colvin Boulevard and Read
Avenue), which remained unrepaired for a number of weeks during
the latter part of the study period, the observed slight ground-
water mound near the northern portion of the canal probably sig-
nifies that the shallow system had not yet fully returned to
equilibrium at the time of water-level measurements in that gen-
eral vicinity. The slight ground-water depression near the
southern end of the landfill was probably caused by the remedial
measures instituted at Love Canal.
In most locations, the computed hydraulic head of the shal-
low system was found to be nearly equal to the hydraulic head in
the dolomite. Therefore, it is likely that the hydraulic heads
measured in the shallow system are dependent on highly local
variations in permeability, in recharge, in evapotranspiration,
and in discharge to the creeks and rivers. These factors prob-
ably help to account for the features noted in the figure. Due
to the low permeability and heterogeneous nature of the overbur-
den, ground-water movement in the overburden is generally very
slow except in highly localized areas of more permeable material.
4.1.3.2 Ground-Water Flow Modeling
An extensive report on the modeling of ground-water movement
in the general Love Canal area was mentioned earlier as being
available from NTIS. Some of the major findings from the model-
ing effort are restated here.
1. In the general Love Canal area the vertical movement
through the confining bed separating the overburden and
dolomite aquifers is very low with vertical velocities on
the order of 0.001 inches/year.
2. Assuming a downward movement through the confining bed
(although the heads probably fluctuate seasonally), and
that the confining bed was not breached during excavation
and does not contain fracture zones, it would take a non-
attenuated contaminant hundreds to thousands of years to
migrate down to the dolomite. If attenuation occurs, as
is likely, travel time will increase.
71
-------
567J
570.1
564.9
567.2
56
564S
564.6
564,7
564.0
563.6
9.8
570
570.:
564.8 5643
563.8
5652
56
56i.6
566.0
565.4 5g7
5®<
\ 563'4 562
\ \^ 56
9
i
563.2
1,9
1 5
560.6
•'«
j6566.
uri
51.6
"
\\ "H.
5652
569.5
57
572.2
568.9
562.9
564
568.2
56
5655
563.7
\ \ 567j559^S
L,«INrtU
XAREA
5.6
567.6
0.0 566.3
563'3 565.3
6
5633 562"6
S65'° 569.4
1 .7 569.3
568.6
sesa
564.8
565.4
565.4
566.2
563.6\
569.0
\ \
NOTE: VALUES REPORTED ARE IN FEET ABOVE MEAN SEA LEVEL.
Figure 19. Overburden Static Water Table.
72
-------
3. It was estimated that ground water could migrate through
the overburden at rates ranging from up to approximately 1
foot/year in the less permeable material, to up to approx-
imately 60 feet/year in the more permeable material. How-
ever, due to the discontinuous and heterogeneous nature of
the overburden material, the potential attenuation of
organic contaminants in clayey soils, and the construction
of sewer systems virtually around the entire landfill, it
is highly unlikely that contaminated shallow system
ground-water migrated beyond ring 1 houses.
4. Selective contamination of certain ring 1 houses by
ground-water movement prior to remedial construction was
likely to have occurred as a function of random deposits
of more permeable material in the overburden (for example,
sand lenses and filled swales), and man-made construction
activities (for example, a backyard catch basin and drain-
age pipe); overland flow of contaminants to certain ring 1
houses was a likely mechanism of transport prior to reme-
dial construction when pools of surfaced chemicals were
present at the site.
5. The barrier drain system installed around the landfill was
found to be an effective remedial measure to contain the
outward migration of Love Canal contaminants in the shal-
low system. The barrier drain system will also cause most
shallow system ground water that may have migrated from
the landfill over the past 30 years to locations outside
the barrier drain system (through relatively high perme-
ability soil pathways), to flow towards the drain system
for eventual collection and subsequent treatment in the
Leachate Treatment Facility.
4.1.4 Implications of the Hydrogeologic Program Findings
The implications of the hydrogeologic program findings are
of significant importance in understanding the extent and nature
of the environmental contamination problems at Love Canal. His-
torically speaking, it is clear that contamination of the envi-
ronment occurred in the area immediately surrounding the former
canal. Prior to remedial construction, local residents were sub-
jected to potential exposure to Love Canal contaminants from a
variety of environmental sources: (1) the overland flow of chem-
icals that formed in pools around the site; (2) the volatiliza-
tion and airborne transport of surfaced contaminants? and (3) the
highly selective ground-water transport of contaminants from the
former canal to certain ring 1 houses.
Furthermore, it is clear that (prior to remedial construc-
tion) contamination had entered nearby buried utilities and had
probably been transported considerable distances from the former
canal. In particular, transport occurred through the storm sewer
73
-------
lines around Love Canal, which subsequently contributed to the
contamination of local creeks and rivers by virtue of their dis-
charge into those waterways. The historically active mechanisms
that likely contributed to storm sewer contamination were noted
previously as including: (1) the collection of surfaced contami-
nants which were transported by precipitation run-off to curb
drains surrounding the site; (2) the infiltration of contaminants
into storm sewer lines located adjacent to the landfill (for ex-
ample, ground-water transport may have occurred more readily to
the laterals on Read and Wheatfield Avenues and through specific
permeable soil pathways to storm sewer lines on 97th and 99th
Streets),- (3) the discharge to storm sewers of contaminants
taken-up by sumps in certain ring 1 houses that had been sub-
jected to contamination by ground-water transport and/or overland
flow; (4) the discharge of contaminants taken-up by the French
drain surrounding the 99th Street Elementary School; and (5) the
infiltration and collection of surfaced contaminants in the catch
basin located near the landfill at 949-953 97th Street. As a re-
sult of remedial actions conducted at the site during 1978 and
1979, it is likely that only residual contamination remains in
the nearby sewer systems.
Based on the findings of the hydrogeologic program, the fol-
lowing implications are offered regarding the likely extent and
degree of environmental contamination at Love Canal.
1. Contamination in the shallow system will likely be con-
fined primarily to the Canal Area, with contamination
movement occurring selectively along discontinuous, more
permeable, soil pathways.
2. Contamination in the bedrock aquifer (directly attribut-
able to Love Canal) is not likely, unless the glacial till
was breached during excavation activities.
3. Contamination of other environmental media is highly un-
likely outside of ring 1, except as impacted by storm
sewer transport of contaminants.
4. Contaminated soil, directly attributable to the migration
of contaminants from Love Canal, will likely be present
only in ring 1. Contamination in soil will likely be
greatest where both overland flow and ground-water trans-
port contributed to the migration of contaminants from the
former canal. {From historical evidence and the direction
of ground-water movement, contaminated soil is likely to
be higher south of Wheatfield Avenue, and probably on the
97th Street side, than elsewhere). Contaminated soil out-
side of ring 1, if found, probably resulted from other
causes or from use of contaminated fill materials (that
is, it is unlikely to be related directly to Love Canal).
74
-------
5. Contaminated sumps, directly attributable to the migration
of contaminants from Love Canal, will likely be present
only in certain ring 1 houses where soil conditions per-
mitted the more ready ground-water transport of contami-
nants. As a result of ground-water flow patterns, contami-
nation in sumps is likely to be higher on the southwestern
side (97th Street south of Wheatfield Avenue) of Love
Canal than elsewhere.
6. Contamination is likely present in storm sewers and in
area creeks and rivers near storm sewer outfalls, and is
likely to be residual (prior to remedial construction)
contamination. As a result of likely transport mechanisms
that were operative prior to remedial construction, con-
tamination will probably be higher in storm sewer lines on
97th Street, and in area waterways near outfalls fed by
the 97th Street storm sewer line, than elsewhere.
7. Because the majority of organic compounds deposited in
Love Canal are attenuated by clay (as opposed to being in
aqueous solution), ground-water transport and other water-
borne transport will likely be retarded. As a result, col-
located water and sediment samples will likely reveal
higher levels of contamination in the sediment than in the
water (when contamination is present).
8. Because the former canal has been capped since 1979, which
has altered the hydrogeological characteristics of the
landfill, contamination in air directly attributable to
Love Canal will likely not be present in the Declaration
Area. It is likely that only certain, selectively con-
taminated ring 1 residences will display evidence of air
contamination that is directly attributable to Love Canal,
and incrementally significant above background. Further-
more, it is likely that air contamination in the vast
majority of ring 1 residences was terminated in 1979, as a
result of the completion of remedial actions at the site
and the simultaneous cessation of sump pumps operating in
Canal Area residences in 1979.
4.2 EVIDENCE OF CONTAMINATION MOVEMENT
The monitoring efforts at Love Canal were conducted by EPA to
obtain evidence regarding the migration of contaminants from the
former canal into the surrounding Declaration Area. The results
of these studies are presented in this section of the report. In
Table 6, a summary of the magnitude of the multimedia monitoring
efforts designed to identify evidence of chemicals migrating from
Love Canal is presented. The data in Table 6 enumerate for each
medium/source/location sampling combination the total number of
analytes determinations, the number of samples analyzed (note
that this number does not necessarily refer to the number of
75
-------
TABLE 6. FREQUENCY OF DETECTION OF CONTAMINANTS IN
VALIDATED LOVE CANAL SAMPLES
Declaration Area
Medium/Source/
Location
Ground Water
Shallow
Bedrock
Soil
Sump Water
Sump Sediment
Sanitary Sewer
Water
Sanitary Sewer
Sediment
Storm Sewer Water
Storm Sewer
Sediment
Surface Water
Stream Sediment
Air
HIVOL
PFOAM
TENAX
Deter-
minations^
(Samples)
6,675
(233)
4,966
(179)
22,361
(753)
18,752
(694)
0
(0)
152
(6)
74
(1)
1,612
(87)
2,399
(116)
2,268
(84)
2,538
(79)
1,088
(109)
10,865
(636)
21,082
(896)
Percent
Detect
8.5
8.4
9,4
10.2
—
22.4
62.6
8.3
15.5
7.1
21.3
45.3
6.3
36.5
Control
Deter-
minations Percent
(Samples) Detect
1,580 9.0
(55)
2,688 8.5
(94)
1,607 9.7
(57)
650 10.2
(23)
0
(0)
0
(0)
0
(0)
142 3.5
(5)
76 18.4
(2)
727 5.8
(28)
746 14.6
(22)
0
(0)
541 6.1
(32)
791 40.2
(34)
Canal
Deter-
minations
(Samples)
2,438
(81)
1,859
(67)
4,442
(158)
2,432
(97)
159
(6)
0
(0)
0
(0)
344
(17)
637
(28)
0
(0)
0
(0)
89
(9)
1,232
(74)
2,006
(108)
Area
Percent
Detect
10.6
6.2
10.4
14.4
36.5
__
—
10.2
28.3
—
—
41.6
6.3
36.3
Total number of specifically targeted chemicals analyzed for in all com-
bined validated samples
Note: Inorganic substances represent approximately the following percent
of the determinations in the medium/source identified: water, 9;
sediment, 9; soil, 9; and HIVOL, 100.
76
-------
sites sampled), and the percent of the analytes determinations
that were identified at a trace or greater concentration. (See
Appendixes C through E of this Volume for information on analyti-
cal limits of detection).
The relatively large number of substances monitored at Love
Canal possess a wide range of physical and chemical properties
that are associated with their potential for migrating from the
former canal. In particular, the substances monitored vary
considerably in terms of solubility, vapor pressure, and sorbtive
behavior; characteristics that are commonly used to indicate the
potential mobility of a chemical in the environment. Based on
these characteristics, the targeted substances include chemicals
that are expected to vary in potential mobility from (relatively)
high to low. As a consequence of the relatively wide range of
chemical and physical properties possessed by the substances
monitored, the likelihood of detecting the presence of Love
Canal-related contamination in the Declaration Area was
increased. Because the targeted substances also represented
those that were most abundant in the source, prevalent in the
environment, and of toxicological concern, and because purposive
sampling was employed along suspected pathways of contaminant
transport, it is highly unlikely that the presence of substantial
amounts of Love Canal-related contamination in the Declaration
Area would have been missed by the monitoring program.
In the sections that follow the results from the monitoring
program conducted at Love Canal are presented. It should be
noted that while all of the monitoring results were considered in
the statements of findings, only a relatively limited number of
substances are presented for discussion purposes. To the extent
possible, a consistent set of chemicals are discussed across all
medium/source/location combinations in order to provide con-
tinuity and comparability to the findings.
4.2.1 Ground-Water Contamination
Evidence of contaminant movement in ground water was obtained
through the installation (described previously) and sampling of a
large number of monitoring wells throughout the general Love Ca-
nal area. Ground-water contamination was monitored separately in
the overburden shallow system (A Wells) and in the bedrock aqui-
fer (B Wells). The findings from these monitoring efforts are
described sequentially. It should be noted that no ground-water
monitoring wells were installed inside the boundary of the bar-
rier drain system encircling the former canal.
4.2.1.1 Shallow System
In general, neither the extent (that is, the relative fre-
quency with which substances were detected at a trace or greater
concentration) nor the degree (the value of the median concentra-
tion measurement for a particular substance) of contamination in
77
-------
the Declaration Area differed significantly (a- 0.10, one-tailed)
from the ground-water contamination observed at shallow system
control sites. Statistically significant differences in the ex-
tent of shallow system ground-water contamination, based on com-
parisons between the Canal Area and Declaration Area, were found
for the substances identified in Table 7. (See Volume III for
additional details). Note, that the results of the statistical
tests reported in Table 7 (and in similar subsequent tables) are
not pair-wise independent. Consequently, the Type I error rate
(that is, the probability of incorrectly rejecting the null hypo-
thesis) is greater than a,
As can be seen from the data summarized in Table 7, and pre-
sented in detail in Volume III, virtually no evidence of shallow
system ground-water contamination was found at sites sampled out-
side the Canal Area. The absence of Declaration Area shallow
system ground-water contamination, that was directly attributable
to the migration of contaminants from the former canal, conformed
to the findings and implications of the hydrogeologic program.
Specifically, the data revealed that contamination of the over-
burden aquifer was confined to the Canal Area, and that within
the Canal Area only selective migration (along more permeable
soil pathways) of contaminants from Love Canal had occurred.
Three examples of typical shallow system findings are pre-
sented in Figures 20 through 22 to illustrate the overburden
ground-water contamination observed at Love Canal. Additional
figures are included in Volume III. The results presented in
Figures 20 through 22 are for benzene, toluene, and "V-BHC (Lin-
dane), respectively. These compounds were selected for presenta-
tion because of their migration properties and because they were
illustrative of shallow system findings, were among the most
frequently detected organic compounds in the shallow system, and
were known waste materials deposited in the former canal. In
Figures - 20 through 22, the maximum concentration of the compound
of interest observed at each site is presented. This procedure
was adopted in order to incorporate the information obtained at
those QA/QC sites where multiple field samples may have been
collected. Consequently, the concentration levels presented in
these figures are likely to be conservative (that is, high)
indicators of the actual concentration levels present in the
shallow system ground water at those sites sampled. Note that in
all figures no systematic evidence was observed of contaminants
that had migrated from Love Canal into the Declaration Area, even
though numerous wells were sited in the Declaration Area along
suspected transport pathways (for example, in or near former
swales).
Additional detailed analyses of the shallow system monitoring
data (using a variety of statistical methods such as correla-
tional analysis, principal components analysis, and cluster
analysis—see, for example, S. James Press, Applied Multivariate
78
-------
TABLE 7. SIGNIFICANT DIFFERENCES OBSERVED IN EXTENT OF SHALLOW
SYSTEM GROUND-WATER CONTAMINATION AT LOVE CANAL
Percent Detect
(Number of Samples)
Compound/Element
2 , 4-Dichlorophenol
2,4, 6-Tr ichlorophenol
1 , 4-Dichlorobenzene
1 , 2-Diehlorobenzene
1,2, 4— Trichlorobenzene
1,2,3, 4-Tetrachlorobenzene
Acenaphthy lene
Fluorene
1 , 1-Dichlorethene
Tetrachloroethene
2-CMorotoluene
3-Chlorotoluene
4-Chlorotoluene
Chlorobenzene
Chromium
Lead
Decl,
2,1
(47)
0.0
(47)
0.0
(47)
0.0
(47)
0.0
(47)
0.0
(47)
4.3
(47)
4.3
(47)
2.3
(43)
2,3
(43)
0.0
(43)
0.0
(43)
0.0
(43)
2.3
(43)
66.0
(43)
72.3
(47)
Control
9.1
(11)
0.0
(11)
0.0
(11)
0.0
(11)
0.0
(11)
0.0
(11)
0.0
(11)
0.0
(11)
0.0
(11)
27.3
(11)
0.0
(11)
9.1
(11)
0.0
(11)
0.0
(11)
70.0
(10)
77.8
(9)
Canal
18,8
(16)
13.3
(15)
12.5
(16)
12.5
(16)
12.5
(16)
12.5
(16)
18.8
(16)
18.8
(16)
14.3
(21)
19,0
(21)
19.0
(21)
10.0
(20)
9.5
(21)
23.8
(21)
92.9
(14)
100.0
(13)
Comparison
Canal - Decl.
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
No (0-0.104)
Yes
Yes
Yes
Decl . - Control
No
No
No
No
No
No
No
No
No
No
No
No
No
NO
No
No
Comparisons based on a one-tailed difference of
exact test, for the areas indicated, and in the
proportions test {a=0.10), using Fisher's
order presented.
79
-------
xB
xT
Legend:
T—Trace
B—Below Detection
N—No Analysis
xB
xB
Figure 20.
Well A Sampling Sites,
Benzene, Maximum Concentrations
(micrograms per liter, ppb).
80
-------
xB
Legend:
T-Trace
B—Below Detection
N—No Analysis
xB
Figure 21. Well A Sampling Sites,
Toluene, Maximum Concentrations
(micrograms per liter, ppb).
81
-------
xO.01
Legend:
T-Trace
B—Below Detection
N—No Analysis
xT
xB
xB
Figure 22.
Well A Sampling Sites,
T-BHC, Maximum Concentrations
(micrograms per liter, ppb).
82
-------
Analysis, Holt, Rinehart and Winston, 1972), revealed that con-
tamination by organic compounds in the shallow system ground
water was restricted to the Canal Area. In fact, the results
showed that only three A Wells, all located within ring 1, were
highly contaminated. The results also suggested that no pattern
of contamination, directly attributable to the migration of or-
ganic compounds from the former canal into the surrounding neigh-
borhood, could be discerned outside of ring 1. That is, no
patterns of shallow system ground-water contamination were found
outside of the Canal Area that corresponded to suspected trans-
port pathways (for example, former swales or sand lenses), or
that indicated the existence of concentration gradients emanating
from the former canal. Furthermore, the infrequent detection of
quantifiable levels of organic compounds in the Declaration Area
occurred ordinarily as geographically isolated instances of con-
tamination, and did not display systematic detection patterns
across compounds. Because all three highly contaminated shallow
system ground-water sites are located on what is now NYS-owned
property, their addresses are identified here: well 104A was
located in a suspected former swale and near the barrier drain in
the lot south of 754 99th Street; well 77A was located in a known
sand lens and near the barrier drain in the backyard of 775 97th
Street; and well 75A was located in a suspected former swale and
near the barrier drain in the lot at the southwest corner of 99th
Street and Colvin Boulevard. A total of 46 A Wells (out of the
79 sampled) had organic contaminants present at only trace or
lower levels.
4.2.1.2 Bedrock Aquifer
In general, neither the extent nor the degree of bedrock
aquifer contamination in the Declaration Area (or in the Canal
Area) differed significantly (a =0.10, one-tailed) from the
ground-water contamination observed at bedrock aquifer control
sites. Furthermore, the levels of contamination observed in the
bedrock aquifer were generally very low, displayed random pat-
terns of occurrence, and did not reveal plumes of contamination
that directly emanated from Love Canal.
Three examples of typical bedrock aquifer results are pre-
sented in Figures 23 through 25 to illustrate the Lockport Dolo-
mite ground-water contamination observed in the general Love
Canal area (additional figures are included in Volume III). The
organic compounds displayed in Figures 23 through 25, benzene,
toluene, and Y-BHC (respectively), were selected because of their
migration properties and because they were illustrative of bed-
rock aquifer findings, were among the most frequently detected
compounds in the bedrock aquifer, and were known waste materials
present in the landfill. As before, the maximum concentration of
the compound of interest observed at each site is presented.
83
-------
xT
Legend:
T-Trace
B—Below Detection
N-No Analysis
xB
xB
Figure 23.
Well B Sampling Sites,
Benzene, Maximum Concentrations
(micrograms per liter, ppb).
84
-------
x16
Legend:
T-Trace
B-Below Detection
N-No Analysis
xB
I
xB
Figure 24.
Well B Sampling Sites,
Toluene, Maximum Concentrations
(micrograms per liter, ppb).
85
-------
xB
Legend:
T—Trace
B—Below Detection
N—No Analysis
xB
xfl
Figure 25.
Well B Sampling Sites,
Y-BHC, Maximum Concentrations
(micrograms per liter, ppb).
86
-------
It can be seen in Figures 23 through 25 that no clear pat-
terns of Love Canal-related bedrock aquifer contamination were
suggested by the data. Rather, the data revealed that very
low-level, wide-spread contamination in the bedrock aquifer was
likely present, and that the source {or sources) of the contami-
nation observed in the aquifer could not be identified. In par-
ticular, the data revealed that anomalous up-gradient contamina-
tion was present in the aquifer at substantial distances from
Love Canal. The data also suggested that no clear evidence
existed of an incremental contribution to bedrock aquifer contam-
ination which could be directly attributed to the migration of
contaminants from Love Canal into the aquifer.
The absence of clear, consistent evidence demonstrating the
migration of contaminants from the former canal into the bedrock
aquifer conforms to the findings of the hydrogeologic program.
Furthermore, these findings provide indirect support to the in-
ference that the glacial till under the former canal was not
likely breached as a result of excavation or dumping activities.
Additional detailed analyses of the bedrock aquifer moni-
toring data suggested that the observed low-level organic contam-
ination found in bedrock ground-water samples was both widespread
and nonsystematie; that is, contamination was observed up-gradi-
ent and at substantial distances from the former canal. In par-
ticular, it was observed that all of the bedrock monitoring wells
located closest to Love Canal (that is, in the Canal Area) had
only low-level organic contamination present (with total concen-
trations less than 100 parts per billion—micrograms per liter),
and that bedrock monitoring wells located in the Canal Area en-
circled the landfill. Given the southerly direction of ground-
water movement in the Lockport Dolomite near Love Canal and the
lack of clear evidence of a plume of contamination in the bedrock
aquifer that originated in the Canal Area, it is likely that con-
tamination observed in the aquifer was not directly related to
the migration of contaminants from Love Canal. A total of 21 B
wells (out of the 57 sampled) had organic contaminants present at
only trace or lower concentration levels.
4.2.2 Soil Contamination
The extent and degree of soil contamination at Love Canal was
determined through the collection of soil samples at 171 sites
(Figure 26), and the analysis of those samples for the targeted
substances listed in Appendix A. Soil sampling sites were often
intentionally located along suspected transport pathways, includ-
ing former swales, sand lenses, and wet/dry areas. In addition,
sites were located at places where residents reported the sus-
pected presence of chemical contamination, the deposition of fill
materials thought to have been removed from the Canal Area, or
the deposition of fill materials thought to be chemical-industry
wastes. Soil samples were also intentionally collected at each
87
-------
X X
02024 02025
02026
02027 x
02028
x06014 x07014
X07004
1102506001070111
xix ix x07017
xO?Q13
1 x07801
X11015
CANAL
AREA 11Q22x.
06015x
.08011
11003x
11023 1
xl 06003
* P7Q16
x
97814 x01031
9755Qx*
03505 03502x
03506x
X03B08
03507x
X09001
x09012
xnftrms x10028
X10016
J09013J x10014
x10022
Figure 26. Soil Sampling Site Codes.
88
-------
base residence for the purpose of multimedia monitoring. And
finally, in order to assure that the soil samples collected ade-
quately represented the entire general Love Canal area, sites
throughout the Declaration Area and Canal Area were randomly se-
lected (that is, with equal probability) for sampling. It should
also be noted that no soil samples were collected inside the
boundary of the barrier drain system encircling the former canal.
Soil sampling at each site was conducted as follows. Because
it was not possible to stipulate ahead of time the depth at which
contaminants migrating from the landfill might be located in the
soil, but with knowledge that the top 6 feet of soil typically
included nearly all of the more permeable soil material, it was
decided that the entire top 6 feet of soil would be sampled. The
device used to sample soil was a truck-mounted soil corer, 6 feet
in length and 1 3/8 inches in diameter. Because it was not pos-
sible to stipulate ahead of time the likely geographical distri-
bution of contaminants at a given sampling site, it was decided
that at each sampling site a total of seven soil cores would be
collected. Of the seven soil cores collected at each site, two
cores were appropriately handled, and subsequently analyzed sepa-
rately for volatile organic compounds. The remaining five soil
cores were homogenized, and subsequently analyzed for the addi-
tional targeted substances of interest. A typical soil sampling
scheme employed at Love Canal is presented in Figure 27; note,
however, that the actual sampling configuration used at a site
was dependent on the size of the area available for sampling.
The results from the soil monitoring program revealed a pat-
tern of Love Canal-related environmental contamination that was
consistent with the findings of the hydrogeologic program, and
corresponded to the ground-water monitoring findings. In general,
the patterns of soil contamination that were observed revealed
that contaminants had migrated directly from the former canal to
the immediate vicinity of certain ring 1 residences. In particu-
lar, evidence of soil contamination that was directly attribut-
able to the migration of contaminants from Love Canal was found
near: (1) those ring 1 residences that were suspected of having
been subjected to the overland flow of contaminants from the
landfill prior to remedial construction; and (2) those ring 1
residences that had been constructed in the vicinity of more per-
meable soil pathways conveying through-ground migration of con-
taminants from the landfill prior to remedial construction. A
summary of the statistically significant soil monitoring findings
is presented in Table 8. Again, recall that the Type I error rate
is larger than a.
As can be seen from the results presented in Table 8, and
from a review of the detailed tables included in Volume III, the
soils monitoring data revealed that Love Canal-related environ-
mental contamination was confined to the Canal Area. Supporting
89
-------
30-FOOT
CIRCLE
CORES ANALYZED FOR VOLATILE ORGANICS
CORES COMPOSITED AND ANALYZED FOR OTHER
SUBSTANCES
Figure 27.
Typical Soil Sampling Configuration
Used at Each Site.
90
-------
TABLE 8. SIGNIFICANT DIFFERENCES OBSERVED IN EXTENT OF SOIL
CONTAMINATION AT LOVE CANAL
Compound/Element
Phenanthrene
a-BHC
6-BHC
"V-BHC (Lindane)
Heptachlor epoxide
Endrin
DDT
1, 1-Dichloroethene
Chloroform
3-Chlorotoluene
Chlorobenzene
Cadmium
Percent Detect
(Number of Samples)
Decl. Control Canal
23.8
(105)
8.3
(109)
10.1
(109)
6.4
(109)
0.9
(109)
9.2
(109)
5.5
(109)
2.3
(213)
19.2
(213)
0.0
(213)
1.4
(212)
4.6
(108)
44.4
(9)
0.0
(9)
0.0
(9)
0.0
(9)
0.0
(9)
0.0
(9)
0.0
(9)
0.0
(17)
41.2
(17)
0.0
(17)
0.0
(17)
0.0
(9)
39.1
(23)
26.1
(23)
39.1
(23)
21.7
(23)
8.7
(23)
26.1
(23)
21.7
(23)
17.8
(45)
42.2
(45)
4.4
(45)
6.7
(45)
39.1
(23)
Comparison'
Canal - Decl. Decl. - Control
No (a =0.1 08)
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
No
No
No
No
No
No
No
No
No
No
No
No
^Comparisons are .based on a one-tailed difference of proportions test (a=0.10), using
Fisher's exact test, for the areas indicated, and in the order presented.
-------
this finding was the observation that patterns of soil contamina-
tion detected in the Canal Area were often also in relatively
close correspondence with the occurrence of shallow system
ground-water contamination at Love Canal.
Even though direct evidence of Love Canal-related soil con-
tamination was found in the Canal Area, relatively few statis-
tically significant differences in the extent of soil contamina-
tion occur when the Canal Area is compared to control sites. This
result was considered a likely consequence of: (1) the generally
limited through-ground migration of substances from the former
canal (recall that no soil samples were collected inside the
boundary of the barrier drain system? (2) the preferential
through-ground migration of substances from the former canal
along relatively local, narrow, more-permeable soil pathways; (3)
the selective overland flow of contaminants from the former canal
that occurred prior to remedial construction (it was not possible
to estimate the ameliorating effects of microbial degradation on
either the extent or degree of soil contamination observed at
Love Canal); and (4) the relatively small number of soil samples
collected at control sites which limited the power of the statis-
tical test employed. In addition, the relatively infrequent oc-
currence of quantifiable soil monitoring results also rendered a
determination of differences in the degree of soil contamination
found at Love Canal statistically impractical.
In Figures 28 through 31, four examples of soil monitoring
findings are presented to illustrate the typical patterns of soil
contamination found in the general Love Canal area (additional
figures are included in Volume III), The substances displayed in
these three figures are (respectively) benzene (from both of the
two soil cores collected at each site for volatile organics),
y-BHC, and cadmium. As before, the maximum concentration of the
substance of interest observed at each site is presented. From
the results displayed in these figures it can be seen that soil
contamination, which was directly attributable to contaminants
having migrated from Love Canal, was confined to the Canal Area.
Furthermore, no consistent patterns of contamination migrating
out of the Canal Area were found in the soil monitoring data.
Additional detailed analyses of the soil monitoring data
revealed that soil contamination which was directly attributable
to the migration of contaminants from Love Canal was confined to
the Canal Area. In particular, substantial Canal Area soil con-
tamination was prevalent at site 11018 (741 97th Street), which
was the soil sampling site located closest to the known sand lens
on the 97th Street side of Love Canal, and at site 11005 (684
99th Street), which was located in the former major swale that
crossed Love Canal. Both of these sites are located in ring 1.
92
-------
Legend:
T-Trace
B-Below Detection
N-No Analysis
Figure 28. Soil Sampling Sites (First),
Benzene, Maximum Concentrations
(micrograms per kilogram, ppb).
93
-------
Legend:
T-Trace
B—Below Detection
N-No Analytis
CANAL
AREA
5
xB
xB ..r
xB
xB
I, XB
1 xB
•L
^\
^^^
^ ^^^
xB
xE
xB
M
xN
xB
xB
xB
o X
xB
xB
xB
xB
xB
xB
KB
xB
xN x
xN
3 xB
xB
xBXB
xB
xB
xB
xB
xB
xB
xB
xN
xT
xT
xB
xT
xT
xN
Figure 29.
Soil Sampling Sites (Second),
Benzene, Maximum Concentrations
(micrograms per kilogram, ppb) ..
94
-------
Legend:
T-Trace
B-Below Detection
N—No Analysis
Figure 30.
Soil Sampling Sites,
Y-BHC, Maximum Concentrations
(micrograms per kilogram, ppb)
95
-------
Legend:
T—Trace
B—Below Detection
N—No Analysis
Figure 31. Soil Sampling Sites,
Cadmium, Maximum Concentrations
(micrograms per kilogram ppb).
-------
Even though relatively prevalent soil contamination was also
observed at a few other sites, the absence of compelling evidence
revealing a gradient of soil contamination emanating from Love
Canal towards those sites, suggested that the observed contamina-
tion was not due to the natural migration of contaminants from
the landfill. Rather, it is likely that soil contamination found
in the Declaration Area occurred from other causes because no
pattern of soil contamination was found outside of the Canal Area
that corresponded to the shallow system ground-water gradient,
and only isolated instances of soil contamination were found in
the Declaration Area (and these were often at substantial dis-
tances from the former canal). A total of 10 soil sampling sites
(out of the 171 sampled) had organic contaminants present at only
trace or lower concentration levels.
4.2.3 Sump Contamination
The objective of the sump monitoring program was to provide,
through indirect means, additional evidence of Love Canal-related
environmental contamination involving shallow system ground water
and soil. Such indirect evidence would be obtained whenever Love
Canal-related contamination was found present in sump water sam-
ples. In order to attribute sump contamination to the migration
of contaminants from Love Canal, the monitoring program was de-
signed to assist in demonstrating that contamination migrating
from Love Canal had been taken-up from the ground water by base-
ment sumps, and was not present due to other causes. Furthermore,
it was recognized that contaminated basement sumps could also
serve as sources of potential human exposure to toxic substances
that might pose a threat to human health. Because human exposure
to contaminants taken-up by basement sumps could also occur by
inhalation of volatilized airborne pollutants, a special program
of sump/basement-air monitoring was designed and conducted at
Love Canal.
The sump was stirred to obtain a sample of the entire sump
contents, because the amount of sediment present in sumps was not
ordinarily adequate for sampling purposes (except for a few Canal
Area residences). These sump water samples were collected rou-
tinely and analyzed for the targeted substances identified in
Appendix A. At two Canal Area residences (site 11072 at 771 97th
Street, and site 11071 at 779 97th Street), sufficient amounts of
sediment were present in the sumps and both sump water and sump
sediment samples were collected and analyzed for targeted sub-
stances. At each of the base residences, sump water samples were
collected at the same time, and with approximately the same fre-
quency, as the regular air monitoring campaigns were conducted.
In other sites at which sumps were sampled only one routine col-
lection of sump water samples was performed.
97
-------
An initial undisturbed sample of water was collected at all
sump sampling sites for the determination of targeted volatile
organic compounds. Subsequent to the collection of this sample,
the sump was vigorously agitated with a paddle for 2 minutes to
simulate the turbulence caused by the activation of a sump pump.
Additional samples of sump water were then collected for the
analysis of other targeted substances.
The extent and degree of sump water contamination at Love Ca-
nal was determined through the collection and analysis of sump
water samples from 54 sites (Figure 32). As with other environ-
mental media sampled at Love Canal, sump sampling sites were
selected to satisfy a number of different criteria: (1) sites
were often intentionally selected (when in existence and avail-
able for sampling) along suspected preferential soil transport
pathways; (2) sumps were sampled in residences where the occu-
pants reported the suspected presence of contaminants; (3) sumps
were repetitively sampled in each base residence for the purpose
of multimedia monitoring; and (4) sumps were randomly (with equal
probability) selected for sampling from throughout the entire
Declaration Area. In addition to the samples collected at multi-
media monitoring sites, nine sites in the Canal Area were sampled
as part of the previously mentioned special sump/basement-air
study. Due to program constraints and limited voluntary access to
residences outside of the Declaration Area, only one control site
sump (located in a residence on Grand Island) was sampled.
The results from the sump monitoring program revealed a pat-
tern of environmental contamination consistent with the findings
of the hydrogeologic program, and corresponding to both the
ground-water and soil monitoring findings. The pattern of sump
contamination observed revealed that substantial amounts of con-
taminants had preferentially migrated directly from Love Canal
prior to remedial construction and been taken-up by sumps located
in certain ring 1 residences. In particular, evidence of residu-
al sump water contamination (and in two instances, evidence of
high residual sump sediment contamination), that was directly at-
tributable to the migration of contaminants from Love Canal, was
found in: (1) those ring 1 residences that were suspected of
having been subjected historically to the overland flow of con-
taminants from the landfill prior to remedial construction; and
(2) those ring 1 residences that had been constructed in the vi-
cinity of more permeable soil pathways conveying through-ground
migration of contaminants from Love Canal prior to remedial con-
struction. Due to a lack of appropriate historical data, it was
not possible to determine the amount of the residual contamina-
tion observed in these ring 1 sump samples that had been degraded
through natural processes. It is important to note that the sump
pumps in all Canal Area residences which were sampled had been
disconnected and inoperable since 1979, at least 1 year prior to
EPA monitoring. A summary of the statistically significant sump
water monitoring findings is presented in Table 9. Once again,
note that the Type I error rate is larger than a.
98
-------
x97303
97302 x
97300X 973X01
97003 x
10027x
Figure 32. Sump Water Sampling Site Codes,
97534 x
99
-------
TABLE 9. SIGNIFICANT DIFFERENCES OBSERVED IN THE EXTENT OF
SUMP WATER CONTAMINATION AT LOVE CANAL
O
O
Percent
(Number of
Compound
2-Nitrophenol
Phenol
4-Chloro-3-methylphenol
Hexachloroethane
1 , 4-Dichlorobenzene
1 , 3-Dichlorobenzene
1 , 2-Dichlorobenzene
Hexachlorobutadiene
1,2, 3-Trichlorobenzene
1,2, 4-Trichlorobenzene
Naphthalene
2 , 4-Dichlorotoluene
Hexachlorobenzene
Decl.
0.0
(104)
4.8
(104)
0.0
(104)
0.0
(103)
11.5
(104)
1.9
(104)
0.0
(104)
0.0
(104)
0.0
(104)
0.0
(104)
6.7
(104)
0.0
(104)
1.0
(104)
Detect
Samples )
Control Canal
0.0
(4)
0.0
(4)
0.0
(4)
0.0
(4)
0.0
(4)
0.0
(4)
0.0
(4)
0.0
(4)
0.0
(4)
0.0
(4)
0.0
(4)
0.0
(4)
0.0
(4)
23.1
(13)
30.8
(13)
15.4
(13)
23.1
(13)
46.2
(13)
53.8
(13)
38.5
(13)
30.8
(13)
15.4
(13)
53.8
(13)
30.8
(13)
23.1
(13)
38.5
(13)
(continued)
Comparison^
Canal - Decl.
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Decl. - Control
No
No
No
No
No
No
No
No
No
No
No
No
No
'Comparisons were based on
exact test, for the areas
a one-tailed difference of proportions test (a=0.10), using Fisher's
indicated, and in the order presented.
-------
TABLE 9 (continual!)
Percent Detect
(Number of Samples)
Compound
Anthracene
1,2,3, 4-Tetrachlorobenzene
Tetrachlorotoluenes
«-BHC
/3-BHC
S-BHC
y-BHC (Lindane)
trans-1 , 2-Dichloroethene
Chloroform
1 , 2-Dichloroethane
Trichloroethene
Benzene
1,1,2, 2-Tetrachloroethane
Decl .
10.6
(104)
0.0
(104)
0.0
(89)
17.1
(105)
17.1
(105)
14.4
(104)
18.1
(105)
0.0
(104)
7,7
(104)
1.0
(104)
1.9
(104)
7,7
(104)
0.0
(104)
Control
0.0
(4)
0.0
(4)
0.0
(4)
40.0
(5)
0.0
(5)
20.0
(5)
20.0
(5)
0.0
(5)
0.0
(5)
0.0
(5)
0.0
(5)
40.0
(5)
0.0
(5)
Canal
38.5
(13)
46.2
(13)
36.4
(ID
42.9
(14)
35.7
(14)
35.7
(14)
50.0
(14)
31.3
(14)
37.5
(16)
12.5
(16)
31.3
(16)
43.8
(16)
18.8
(16)
Comparison^
Canal - Decl.
Yes
Yes
Yes
Yes
No (a =0.102)
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Yes
Decl. - Control
Ho
No
No
No
No
No
No
No
No
No
No
No
No
(continued)
'Comparisons were based on
exact test, for the areas
a one-tailed difference of proportions test (a=0.10), using Fisher1
indicated, and in the order presented.
-------
TABLE 9 (continued)
o
to
Percent Detect
(Number of Samples) Comparison*
Compound
o-Xylene
m-Xylene
Tetrachloroethene
Toluene
2-Chlorotoluene
3-Chlorotoluene
Chlorobenzene
Ethyl benzene
Decl.
1.9
(104)
3.8
(104)
14.4
(104)
16.3
(104)
0.0
(90)
0.0
(90)
1.9
(104)
3.9
(90)
Control
0.0
(5)
0.0
(5)
0.0
(5)
20.0
(5)
0.0
(5)
0.0
(5)
0.0
(5)
0.0
(5)
Canal Canal - Decl. Decl. - Control
25.0 Yes No
(16)
31.3 Yes No
(16)
37.5 Yes No
(16)
43.8 Yes No
(16)
40.0 Yes No
(15)
40.0 Yes No
(15)
37.5 Yes No
(16)
25.0 Yes No
(16)
Comparisons were based on a one-tailed difference of proportions test (o>=0.10), using Fisher's
exact test, for the areas indicated, and in the order presented.
-------
As can be seen from the results presented in Table 9, and
from a review of the tables included in Volume III, the sump wa-
ter monitpring data revealed that direct Love Canal-related
environmental contamination (note, for example, the chlorinated
benzenes and chlorinated toluenes) was confined to the Canal
Area. Supporting these statistical findings was the observation
that patterns of sump water contamination found in the Canal Area
were also ordinarily closely associated with the occurrence of
both shallow system ground-water contamination and soil contami-
nation.
Three examples of typical sump water monitoring results are
presented in Figures 33 through 35 to illustrate the pattern of
sump water contamination found at Love Canal (additional figures
are included in Volume III). The compounds displayed in these
figures are benzene, toluene, and Y-BHC (Lindane), respectively.
As was done previously, the maximum concentration of the compound
of interest observed at each site is presented. In Figures 33
through 35 it can be seen that the pattern of sump water contami-
nation revealed by the data is consistent with the findings of
shallow system ground-water contamination displayed in Figures 20
through 22, and the findings of soil contamination displayed in
Figures 28 through 31. In particular, note that (once again)
evidence of direct Love Canal-related environmental contamination
is restricted to the vicinity of certain ring 1 residences in the
Canal Area.
Additional detailed analyses of the sump monitoring data re-
vealed that sump water contamination directly attributable to the
migration of contaminants from Love Canal was confined to the
Canal Area. In particular, Canal Area contamination was prevalent
at the following sites, all located in ring 1: site 11071 at 779
97th Street; site 11070 at 783 97th Street; site 11072 at 771
97th Street; site 11021 at 476 99th Street; site 11073 at 703
97th Street; and site 11005 at 684 99th Street. It is noteworthy
that the three most highly contaminated sumps (identified by the
sump water monitoring data) were located: (1) in those ring 1
residences closest in proximity to the known sand lens located on
the western side of Love Canal, south of Wheatfield Avenue; (2)
near the highly contaminated shallow system well number 77A,
which was installed through the known sand lens in ring 1 at 775
97th Street; and (3) near the highly contaminated ring 1 soil
sampling site 11012 at 741 97th Street, which was the soil sam-
pling site located closest to the sand lens. In addition, evi-
dence of both sump water contamination and soil contamination
were identified at site 11005 (684 99th Street), which was previ-
ously noted as being located along the former major swale that
crossed Love Canal. (See Figures 2 and 14). Of the 54 sites sam-
pled for sump water contamination, a total of 11 sites had organ-
ic contaminants present at only trace or lower concentration
levels.
103
-------
Legend:
T-Trace
B—Below Detection
N—No Analysis
t
xB
Figure 33.
Sump Water Sampling Sites,
Benzene, Maximum Concentrations
(micrograms per liter, ppb).
104
-------
xB
Legend:
T-Trace
B—Below Detection
N—No Analysis
Figure 34.
Sump Water Sampling Sites,
Toluene, Maximum Concentrations
(micrograms per liter, ppb).
105
-------
-N-
Legend:
T-Trace
B—Below Detection
N-No Analysis
xB
xB
xB
Figure 35.
Sump Water Sampling Sites,
7-BHC, Maximum Concentrations
(micrograms per liter, ppb).
106
-------
Because only two sump sites were found to have sufficient
sediment present for sampling and analysis purposes, an extensive
discussion of the monitoring results obtained is unnecessary. The
reason for this is because it is sufficient to note that at sump
sampling sites 11071 (779 97th Street) and 11072 (771 97th
Street), where both sump water and sump sediment samples were
collected, high contamination of both media was present.
Now, it is well known that many of the organic compounds
monitored at Love Canal are both hydrophobic and readily sorbed
on sediments. That is, their equilibrium sorption behavior, as
characterized by the partition coefficient Kp or Koc , is rela-
tively high? see, for example, S. W. Karickhoff, "Semi-Empirical
Estimation of Sorption of Hydrophobic Pollutants on Natural Sedi-
ments and Soils," Chemosphere, Vol. 10 (1981), 833-846. There-
fore, it was not surprising to find the presence of highly con-
taminated (solution phase) sump water in association with the
presence of very high concentrations (sorbed phase) of certain
organic contaminants present in the sump sediment (particularly
since the sump water had not been refreshed by pumping, and
consequently diluted, since 1979). The reader interested in the
specific results obtained from the analysis of sump sediment
samples is referred to Volume II.
Before concluding this section it is perhaps worth mentioning
again that, prior to remedial construction in 1979, Canal Area
basement sumps were discharged into the local storm sewer lines
on 97th and 99th Streets. The likely consequences of this activ-
ity on the distant transport of contaminants from Love Canal into
the surrounding environment are discussed in the next two sec-
tions of the report.
4.2.4 Sanitary and Sto r m S e we r Con t am ina t ion
Samples of sanitary sewer water and sediment were collected
from the Love Canal Declaration Area access point located at the
intersection of Wheatfield Avenue and 101st Street (site 08016,
see Volume II). This particular sampling location was selected
because it was directly connected to the portion of the sanitary
sewer line that was installed across the landfill, under Wheat-
field Avenue, by the City of Niagara Palls in 1957. In addition,
the location selected was sufficiently far from Love Canal to
(potentially) provide evidence of the distant transport of in-
filtrated contaminants. Because the sanitary sewer line under
Wheatfield Avenue was encompassed by the barrier drain system in
1979 and plugged at 99th Street by the city in early 1980, it was
deemed likely that any residual contamination present in the line
would be due to historical transport.
Prom the analysis performed on the sanitary sewer samples
collected, the presence of Love Canal-related contaminants in
both sanitary sewer water and sanitary sewer sediment samples was
107
-------
revealed clearly, with higher concentration levels present in the
sediment samples. In particular, a number of substances detected
in the sanitary sewer samples were identified as indicators of
the direct migration of contaminants from Love Canal (the speci-
fic results may be found in Volume II). For example, in sanitary
sewer water samples a number of chlorinated toluenes were found;
while in sanitary sewer sediment samples, evidence of high con-
tamination was found involving chlorinated benzenes, chlorinated
toluenes, and hexachlorocyclopentadiene (C-56).
A total of 29 sampling sites (identified where possible in
Figure 36) were included in the storm sewer portion of the moni-
toring program. Storm sewer sampling was conducted during the
months of August and October 1980, and involved the collection
and analysis of water and sediment samples (when available in
adequate amounts) for the targeted substances identified in Ap-
pendix A. In a previous section (4.1.1.2) on topography and
drainage, the existence, location, and direction of water-flow in
storm sewer lines in the immediate vicinity of Love Canal was
discussed; they were graphically displayed in Figure 12.
Also discussed in Section 4.1.1.2 was the existence and loca-
tion of certain features that, prior to remedial construction,
may have contributed to the transport of contaminants from Love
Canal into the nearby storm sewers. These included: (1) a French
drain around the 99th Street Elementary School that was connected
to a storm sewer line on 99th Street; (2) storm sewer laterals on
Read and Wheatfield Avenues that were connected to storm sewer
lines on 97th and 99th Streets; and (3) a catch basin at 949-953
97th Street located near the boundary of the former canal that
was connected to a storm sewer line on 97th Street, In addition,
it was noted that prior to remedial construction, the overland
flow of surfaced contaminants may have reached the encircling
streets where they would have been captured by the existing curb
drains.
From that which was discussed previously in Sections 4.2.1
and 4.2.2 it may be concluded that prior to remedial construction
at Love Canal, a potential existed for the migration (through
permeable soil pathways) of contaminants from the former canal
into the storm sewer lines on 97th and 99th Streets, and laterals
on Read and Wheatfield Avenues, As a result of remedial measures
taken at the site, however, it is likely that only residual con-
tamination remains in the affected storm sewer lines. From the
information presented in Section 4.2.3, it must also be concluded
that, prior to 1979, the sumps of certain ring 1 residences
served to collect, and subsequently discharge, contaminants into
the storm sewer lines with which they were connected. Based on
the monitoring evidence presented in Section 4.2.3, it is likely
that the storm sewer line on 97th Street, south of Wheatfield
Avenue, received the greatest amount of contamination through
this mechanism. Furthermore, it is highly unlikely (based on the
108
-------
X09017
x10033
Figure 36. Storm Sewer Sampling Site Codes
109
-------
evidence presented in Sections 4.2.1 through 4.2.3) that storm
sewers sampled in the Declaration Area would display evidence of
direct Love Canal-related contamination, except for those storm
sewers that directly connect to the storm sewer lines originating
on 97th and 99th Streets. Because all storm sewers in the gen-
eral Love Canal area that connect to Canal Area storm sewer lines
were displayed in Figure 12, no additional details on storm sewer
water-flow directions will be presented here.
The evidence obtained from the storm sewer monitoring program
revealed a clear pattern of direct, Love Canal-related contamina-
tion in all storm sewer lines that connect to the storm sewers
originating on 97th and 99th Streets. In general, the patterns
of contamination revealed by the data suggested the occurrence of
decreasing contaminants concentrations with increasing distance
from the Canal Area, in both storm sewer water and storm sewer
sediment samples. Furthermore, the data revealed no evidence of
Love Canal-related contamination in storm sewers sampled that
were isolated from direct Canal Area flow.
In Figures 37 through 41, typical examples of results from
the storm sewer monitoring program are presented. Additional
storm sewer figures are presented in Volume III. In Figure 37
the results obtained for benzene are presented for storm sewer
sediment samples? in Figures 38 and 39 the results obtained for
toluene are presented for storm sewer water and storm sewer
sediment samples, respectively; and in Figures 40 and 41, the
results for "Y-BHC (Lindane) are presented. As can be seen in the
figures, clear evidence of Love Canal-related contamination is
evident in those storm sewers that connect to the 97th and 99th
Streets sewer lines, with high, levels of contamination displayed
in sediment samples. In addition, it is clear from the data pre-
sented in Volume II, and from the figures, that sediment contami-
nation concentration levels were related to accumulation points
in the storm sewers which consist of turning points and junctions
(for examples, sites 11033, 04508, 02501, 04506, and 11031). Pre-
sumably, the relatively low levels of organic contaminants found
in storm sewer water samples was due to the continuing flow of
water in the operating storm sewers (which would dilute the con-
centration levels) , the low solubility in water of some of the
organic compounds monitored, and the preferential sorption of
some of the organic compounds monitored on sediment particles.
Because a considerable amount of additional storm sewer moni-
toring data are similar to that which was just presented, no
other storm sewer data will be offered. The reader interested in
additional details of this monitoring effort may consult Volumes
II and III for more information. Before concluding, however, it
should be noted that numerous Love Canal-related compounds were
found in both storm sewer water and sediment samples, including
chlorinated benzenes and toluenes, and a number of pesticides
such as the four targeted isomers of hexachlorocyelohexane (BHC).
110
-------
xB
Legend:
T-Trace
B—Below Detection
N—No Analysis
Figure 37.
Storm Sewer Sediment Sampling Sites,
Benzene, Maximum Concentrations
{micrograms per kilogram, ppb).
Ill
-------
Legend:
T-Trace
B—Below Dttection
N—No Analysis
Figure 38,
Storm Sewer Water Sampling Sites,
Toluene, Maximum Concentrations
(micrograms per liter, ppb).
112
-------
Legend:
T—Trace
B—Below Detection
N—No Analysis
Figure 39.
Storm Sewer Sediment Sampling Sites,
Toluene, Maximum Concentrations
(micrograms per kilogram, ppb).
113
-------
Legend:
T—Trace
B—Below Detection
N—No Analysis
Figure 40.
Storm Sewer Water Sampling Sites,
T-BHC, Maximum Concentrations
(micrograms per liter, ppb).
114
-------
Legend:
T-Trace
B—Below Detection
N—No Analysis
Figure 41,
Storm Sewer Sediment Sampling Sites,
T-BHC, Maximum Concentrations
(micrograms per kilogram, ppb).
115
-------
4.2.5 Surface Water and Stream Sediment Contamination
Surface waters in the general Love Canal area are identified
in Figures 1 and 3, and were discussed briefly in Section
4.1.1.2. To reiterate, Bergholtz Creek forms the northern bound-
ary of the Declaration Area, and flows from east to west. Black
Creek, which flows from east to west, is located north of Colvin
Boulevard in the Declaration Area, is below grade in a culvert
between 102nd Street and 98th Street, and joins Bergholtz Creek
near 96th Street. The upper Niagara River, which also flows from
east to west, is located approximately 1/4 mile south of the
Declaration Area; a tributary known as the Little Niagara River
circles to the north of Cayuga Island. Bergholtz Creek joins
Cayuga Creek approximately 1/4 mile northwest of the Declaration
Area at a point near the intersection of Cayuga Drive and 88th
Street. Cayuga Creek, which flows from north to south, joins the
Little Niagara River near South 87th Street. Because of the gen-
tle slopes to the beds in Black, Bergholtz, and Cayuga Creeks,
water-flow is known to occasionally experience gentle reversals
due to certain weather-dependent conditions.
Samples of water and sediment were collected from 19 sites
located in the creeks and rivers mentioned previously. The lo-
cation of each site selected for surface water and sediment sam-
pling is presented, where possible, in Figure 42. In addition,
samples of water and sediment were collected from Fish Creek,
north of Niagara University, for control purposes. As can be seen
from the location of surface water and sediment sampling sites
presented in Figure 42, and from the location of storm sewer out-
falls shown in Figure 12, sites in Black Creek and the Niagara
River were intentionally selected in relatively close proximity
to the outfalls. Sites in Black Creek, Bergholtz Creek, the Ni-
agara River, and the Little Niagara River were also sampled down-
stream from Love Canal-related storm sewer outfalls, in order to
obtain some idea of the likely distance that contaminants from
Love Canal may have been transported in those waterways.
Sediment samples were collected in a manner analogous to the
procedure used for collecting soil samples. Namely, a number of
subsamples were collected at a site and homogenized prior to
analysis for targeted substances other than volatile organic com-
pounds. Separate sediment samples were collected for the analy-
sis of targeted volatile organic compounds. A sampling pattern,
dependent on the space available, similar to that displayed in
Figure 27 was used for the collection of sediment samples in
creeks and rivers. Wherever possible, an Ekinan dredge was used
to collect sediment samples; at times, a stainless steel trowel
was used to collect sediment samples when the depth and hardness
of accumulated sediments prohibited use of the dredge.
In Figures 43 through 47, typical examples of the results
obtained from the surface water and stream sediment monitoring
116
-------
I
97026x
X97543 x97537
x97536
Figure 42. Surface Water and Stream Sediment Sampling Site Codes,
117
-------
xB
Legend:
T-Trace
B-Below Detection
N—No Analysis
x7.4
x400
xB
Figure 43. Stream Sediment Sampling Sites,
Benzene, Maximum Concentrations
(micrograms per kilogram, ppb).
118
-------
Legend:
T—Trace
B—Below DetBction
N—No Analysis
I
xB
xT
x35
Figure 44. Surface Water Sampling Sites,
Toluene, Maximum Concentrations
(micrograms per liter, ppb).
119
-------
-N-
Legend:
T-Trace
B—Below Detection
N—No Analysis
xT
x14
x37
x53
Figure 45. Stream Sediment Sampling Sites,
Toluene, Maximum Concentrations
(micrograms per kilogram, ppb).
120
-------
Legend:
T-Trace
B—Below Detection
N-No Analysis
1
xT
xB
xT
xB
Figure 46. Surface Water Sampling Sites,
Y-BBC, Maximum Concentrations
(micrograms per liter, ppb).
121
-------
xB
Legend:
T-Trace
B-Below Detection
N—No Analysis
x34 x2500
x30
Figure 47. Stream Sediment Sampling Sites,
Y-BHC, Maximum Concentrations
(micrograms per kilogram, ppb).
122
-------
program are presented. Additional surface water and stream sedi-
ment figures are presented in Volume III. In Figure 43 the
results obtained for benzene in stream sediment samples are pre-
sented; in Figures 44 and 45 the results for toluene are pre-
sented for water and sediment samples, respectively; and in
Figures 46 and 47, the results for a-BHC are presented. hs can
be seen in these figures, clear evidence of Love Canal-related
contamination was found in Black Creek at, and downstream from,
the 96th Street storm sewer outfall in the creek (sites 04015 and
04016). Because a Canal Area-related storm sewer outfall in Black
Creek is also located in the underground portion of the creek
between 101st and 102nd Streets, the closest point to the outfall
that could be sampled was located downstream where Black Creek
surfaces near 98th Street (site 04014). At this site too, evi-
dence of Love Canal-related contamination was found. Specific
details of the results obtained may be found in Volume II.
The evidence obtained near the 102nd Street outfall (site
97543) was also suggestive of the transport of contaminants from
Love Canal, However, due to the proximity of the 102nd Street
landfill, it was not possible to identify the contamination
present at the site as due totally to the direct migration of
contaminants from Love Canal. In particular, substantial con-
centration levels of identical contaminants were found in sedi-
ment samples collected upstream from the outfall. In passing, it
should be noted that contaminated sediment was also found in both
Cayuga Creek and the Little Niagara River. Given the limited
evidence identifying the existence of mechanisms for the direct
migration of Love Canal-related contaminants to these waterways,
it cannot be concluded unequivocally that the source of contami-
nation is Love Canal.
Before concluding this portion of the report, it may be use-
ful to review the major results obtained thus far. To begin with,
a clear, consistent pattern of ground-water, soil, and sump con-
tamination was found in certain ring 1 residences. In addition,
both the sanitary and storm sewer lines constructed immediately
adjacent to Love Canal were found to be contaminated and were
continuing to contribute to the distant transport of contaminants
from Love Canal. Finally, the evidence obtained also suggested
that creeks and rivers in the immediate vicinity of Love Canal-
related storm sewer outfalls, and for some undetermined distance
downstream from those outfalls, were contaminated by the direct
migration of contaminants from the former canal through the storm
sewer system,
4.2.6 Air Contamination
The air monitoring program was designed to determine the spa-
tial and temporal variability in airborne contamination caused by
123
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pollutants migrating from the former canal. To accomplish this
goal, the selection of a sufficient number of air monitoring
sites and sampling periods had to be balanced against time, bud-
getary, and logistical constraints. Consequently, a sampling de-
sign was selected for air monitoring purposes that involved par-
titioning the Declaration Area into homogeneous units (Figure 4).
The sampling area scheme adopted was intended to categorize the
residences of the Declaration Area according to characteristics
that may have been related to the migration of contaminants from
Love Canal, including distance and direction from the Canal Area,
and proximity to local creeks (Figure 3). In addition, criteria
established for the selection of specific residences within each
sampling area included the following: (1) adjacency to known
former swales; (2) adjacency to historically wet or dry areas
(that is, areas where standing water tended to accumulate); and
(3) all sites had to be unoccupied throughout the duration of the
study period.
A total of 61 sites in the Declaration and Canal Areas, and 4
control sites, were selected for regular air monitoring purposes
(Figure 48). The air monitoring control sites were: site 99020,
located on Stony Point Road, Grand Island; site 99021, located on
West River Parkway, Grand Island; site 99022, located on Pierce
Road, Niagara Falls; and site 99023, located on Packard Road,
Niagara Falls. At each of the regular air monitoring sites, up to
13 daytime air sampling campaigns (consisting of integrated 12-
hour sampling periods) were conducted. Three special air moni-
toring research studies, an air pollutant transport study, a
sump/basement-air study and an occupied/unoccupied study were
also conducted at Love Canal, The data from these special studies
are included in Volume II, but are not considered in detail in
this report.
Prior to the initiation of the air monitoring program, each
sampling site was cleared of certain household items, such as
cleaning products, aerosol cans, and all other organic consumer
products, and was forced-air ventilated for 4 hours. Throughout
the duration of the study, all entry points in each air monitor-
ing residence were secured with evidence tape, and doors were
padlocked to prohibit unauthorized entrance and potential tamper-
ing with sampling equipment.
It should be pointed out that the sampling design used for
indoor air monitoring purposes was based, in part, on the results
obtained from previous air monitoring studies conducted by vari-
ous organizations at Love Canal. These previous studies sug-
gested that (among other things) relatively large variations in
day-to-day indoor air pollutant concentration levels were likely
to be observed, and that such variations were likely to be caused
by a number of factors. For example, variability in indoor air
pollutant concentration levels could be influenced by: (1) rapid
124
-------
xO
X020B:
vf
1003
x1
1004
I bllOOl
_
06
11005x |
xl
bO
)06
xO(
x04514
x06005
b0200t
"-X02056
\
X03520 \-_
CANAL
AREA
X03503
^
X03502
X03519
X07004
xO,7002
!xQ7003
X07005
X06003
06004
b07501
11003 *
b07001
0800409004
xl 1002
x08002
x 10005
K10003
X11006
x09005
08006x X08003
08001b
LEGEND:
b - BASE RESIDENCE
b09001
X09003 x10006
x 10004
Figure 48. Air Sampling Site Codes
125
-------
fluctuations in ambient concentrations? (2) the use or presence
of certain consumer products in a residence (particularly when
occupied residences are sampled)? and (3) differences in the sam-
pling and analytical methodologies used for monitoring purposes.
The air monitoring program employed at Love Canal was designed
specifically to minimize the confounding effects of these types
of problems.
Three different sampling devices were used to collect air
samples in the Love Canal area. For suspended particulates,
high-volume (HIVOL) samplers employing glass fiber filters were
used. The relative volatility of organic vapor phase compounds
required the use of two solid sorbents for monitoring purposes.
The more volatile compounds were collected on TENAX; polyurethane
foam (PFQAM) was used to collect semivolatile compounds in air
and to monitor for 2, 3, 1, 8-TCDD. (See Section 4.3.5). Appendix
A of this Volume lists those compounds and elements for which air
analyses were performed.
High-volume samplers were operated for 24 hours at a flow
rate of 50 cubic feet per minute. TENAX samplers were operated
for 12-hour sampling periods at a flow rate of 30 cubic centi-
meters per minute, and polyurethane foam samplers were also oper-
ated for 12 hours, but at a flow rate of 1,250 cubic centimeters
per minute. On each of the 13 regular daytime sampling periods,
all samplers were started at 6 a.m. TENAX and PFOAM sampling
periods ended at 6 p.m.; the high-volume samplers continued until
6 a.m. the following day. A total of three nighttime 12-hour
sampling periods, immediately preceding regularly scheduled day-
time campaigns, were also conducted at some sites. Nighttime
sampling began at 6 p.m. and lasted until 6 a.m.; the regular 12-
hour daytime samples were collected immediately following the
night samples. As a result of this sampling schedule there were
three occasions in the study for which night/day comparisons and
estimates of 24-hour concentrations could be obtained. The
findings of the night/day air pollution comparisons study re-
vealed that no significant differences were observed.
In nine residences, referred to as base residemces , multi-
media environmental monitoring was performed. In each base resi-
dence three different air monitoring locations were sampled si-
multaneously. The purpose of this design was to permit an over-
all estimate of indoor pollutant levels and to identify potential
pollutant entrance sources. One sampling location, the basement,
was intended to permit estimation of the concentration levels of
organic compounds potentially evaporating from the sump and
through foundations walls. Duplicate samples were collected at a
second sampling location, the first floor living area, was in-
tended to permit estimation of pollutant levels occurring in the
most commonly occupied area of the residence, and for quality
assurance purposes. And finally, a sampling location immediately
outside the residence, just above ground level, was selected to
126
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permit estimation of ambient concentration levels of monitored
substances. All three sampling locations at base residences con-
tained both TENAX and PFOAM samplers. The outside site also
contained a HIVOL sampler. The remaining residences in each
sampling area, and the four control area homes, were sampled only
in the living area.
In Table 10, the statistically significant results obtained
from the air monitoring program are presented. More extensive
tabulations of air monitoring data, describing the extent and
degree of air contamination found in the general Love Canal area,
are presented in Volume III of this report.
As can be seen from the results presented in Table 10, the
extent of indoor air contamination in the Declaration Area was
significantly (a =0.10, one-tailed) greater than at control sites
for o-chlorotoluene (in living area samples), and o-dichloroben-
zene (also in living area samples). It can also be seen in Table
10 that the only other statistically significant difference found
was for chlorobenzene in living area air samples, comparing the
Canal Area to the Declaration Area.
The reader is cautioned to interpret these few significant
results carefully, and to consider the following points. First,
apart from three compounds, detection percentages were low over-
all. For the three compounds detected most frequently, benzene,
toluene, and 1,1,2,2-tetrachloroethylene, a known contamination
problem (described in Appendix E) associated with the sampling
collection medium TENAX was observed (detection percentages for
these compounds on TENAX were, respectively, 95, 86, and 77 per-
cent) . Second, relatively high detection percentages should not
be equated with the occurrence of relatively high concentration
levels. Third, the detection percentages were not found to dis-
play any consistent patterns of spatial variability (for example,
increased detection was not related to decreased distance from
Love Canal). (See Volume III for appropriate tables). Fourth,
due to the large number of sequential statistical comparisons
that were performed, care must be exercised (because of increased
Type I errors) in the interpretation of the few results observed
that satisfied a nominal level of significance. Finally, the lack
of internal consistency (Table 10) exhibited by the few signi-
ficant results obtained suggests that these outcomes may be due
to chance.
In order to characterize the degree of air contamination
found in the Declaration and Canal Areas, the monitoring data
were subjected to a number of different statistical analyses.
First, at each site the maximum observed concentrations (across
all sampling campaigns) of the organic compounds monitored were
determined according to source (that is, TENAX or PFOAM) and
location. Second, the concentration levels of the organic
127
-------
TABLE 10. SIGNIFICANT DIFFERENCES OBSERVED IN THE EXTENT OF AIR
CONTAMINATION AT LOVE CANAL
Sampling Location Comparison^
Outdoors
Basement
Living Area
Compo und
Canal-
Declaration
Canal-
Declaration
Canal- Declaration-
Declaration Control
o-Chlorotoluene
o-Dichlorobenzene
Chlorobenzene
No
No
No
Ho
No
NO
No (a =0.104)
No
Yes
Yes
Yes
No
Percent Detect
(Number of Samples)
Living Area
Compo und
o-Chlorotoluene
o-Dichlorobenzene
Ch 1 o robe n ze ne
Declaration
27. 5
(461)
43. 4
(459)
1. 3
(460)
Control
6.7*
(30)
10.0*
(30)
0.0*
(31)
Canal
37.0
(54)
24. 1
(54)
7.4
(54)
^Comparisons are based on a one-tailed difference of proportions test
(o=0.10), using Fisher's exact test, for the areas indicated, and in
the order presented.
*The reported percent does not differ significantly from zero at the
o=0.05 level.
128
-------
compounds monitored at each site were reviewed (according to sam-
pling campaign) for temporal trends. Third, the median concentra-
tions of the organic compounds monitored at each site were com-
puted according to source and location. And finally, the median
concentrations of the organic compounds monitored at each site
were computed according to sampling campaign. Because quantifi-
able results for organic compounds monitored on PFOAM were so in-
frequent, they are not presented in this report. The reader
interested in the results obtained from both PFOAM and HIVOL
monitoring should consult Volume III for details.
The remainder of this section discusses the air monitoring
results for the three most frequently detected compounds? ben-
zene, toluene, and 1,1,2,2-tetrachloroethylene. It should be
noted once again that these three compounds are known contami-
nants of the collection medium TENAX, and therefore must be
interpreted in the context of the discussion presented in Appen-
dix E (especially in Table E-4). No other organic compounds were
detected frequently enough to permit additional discussion.
To illustrate the results obtained, the maximum concentra-
tions of benzene obtained from air monitoring conducted at each
site, across all regular air monitoring campaigns, are presented
(respectively) for outside, living area, and basement air moni-
toring locations in Figures 49 through 51. Additional figures of
maximum air pollutant concentrations (for selected compounds) are
presented in Volume III. In Table 11, the three highest concen-
trations of certain organic compounds found in air are reported
according to sampling location, and by Declaration, Control, and
Canal Areas,
A review of the results presented in Figures 49 through 51,
the values reported in Table 11, and the additional tables and
figures presented in Volume III, revealed that no consistent pat-
terns were found in the maximum values of air contaminants which
could be directly attributed to the migration of those compounds
from Love Canal. In light of the findings presented in Section
4.1 and other portions of Section 4.2, and the remedial actions
performed at the site, these results are consistent with the
implications of the hydrogeologic program and the other data
obtained from the monitoring program.
Even though maximum concentration levels are often of consid-
erable interest to individuals, because in some way they may be
thought to represent "worst case" estimates of environmental con-
tamination, problems of statistical interpretation exist. Such
problems exist because both the occurrence and the reliability of
the obtained maximum values may be plagued by measurement prob-
lems. To illustrate this point, it is often the case that maximum
129
-------
x13.1 -It-
Legend:
T—Trace
B-Below Detection
N—No Analysis
x6.9
x4.9
Figure 49. Outside Air Sampling Sites,
Benzene, Maximum Concentrations
(micrograms per cubic meter).
130
-------
Legend:
T-Trace
B-Below Detection
N—No Analysis
x5.7
xB.4
xfi.0
x4.7
x7.5
Figure 50. Living Area Air Sampling Sites,
Benzene, Maximum Concentrations
(micrograms per cubic meter).
131
-------
Legend:
T—Trace
8-Below Detection
N—No Analysis
x6.5
x7.4
Figure 51.
Basement Air Sampling Sites,
Benzene, Maximum Concentrations
(micrograms per cubic meter).
132
-------
TABLE 11. THREE HIGHEST CONCENTRATIONS OF SELECTED COMPOUNDS
OBSERVED IN REGULAR AIR MONITORING
(MICROGRAMS PER CUBIC METER)t
OJ
Living Area
Substance
Benzene
Carbon tetrachloride
CMorobenzene
o-Chlorotol uene
p-Chlorotoluene
o-Dichlorobenzene
p-Dichlorobenzene
1,1,2, 2-Tetrachloroethy lene
Toluene
Declaration
Area
40,21,20
77,45,16
3,3,T
8,6,6
5,5,4
68,64,64
25,23,21
104,64,60
92,90,68
Control
39,27,21
4,T,B
B,B,B
6,T,B
T,T,B
T,T,T
4,1, T
142,108,68
68,52,47
Canal
Area
27,15,13
4,4,T
3,T,T
4,2,2.
3,2,2
6,5,T
T,T,T
89,44,32
57,32,27
Basement
Declaration
Area
15,14,14
11,5,3
3,B,B
5,4,4
5,4,4
9,9,6
17,5,4
158,40,37
57,48,42
Canal
Area
12,8,6
B.B.B
B,B,B
2.T.T
2,T,B
T,T,B
B.B.B
30,27,9
32,19,18
Outdoors
Declaration
Area
23, 15,13
4,3,3
3,T,B
4,4,4
4,4,3
T.T.T
T.B.B
20,20,19
19,18,14
Canal
Area
10,9,6
4.B.B
B,B,B
T.T.B
B,B,B
T.B.B
B.B.B
44,36,11
27,23,12
B: Below detection
T: Trace concentration
tThe reader is cautioned to interpret carefully the extreme values reported in this table, and to not
ascribe statistical significance to these results.
-------
concentrations are reported by only one analytical laboratory and
on one particular date, whereas other analytical laboratories may
not report concentration levels anywhere near such maxima (and in
some cases do not even report concentration levels above the lim-
it of detection).
With this caveat aside, the reader may still choose to cau-
tiously compare the values reported in Table 11 to the existing
air pollution standards and recommended work-place limits iden-
tified in Appendix B of this Volume. Such a comparison reveals
that the maximum concentrations observed at Love Canal were often
orders of magnitude less than the corresponding workplace stand-
ards and recommended exposure limits. However, it must be ac-
knowleged that the applicability of comparing workplace standards
and limits (even after conservative adjustments are attempted) to
residential exposure levels is unknown.
The air monitoring data obtained from Love Canal were also
reviewed from a temporal (that is, sampling campaign) perspec-
tive. Typical examples of the results obtained from this effort,
once again for benzene, are presented in Figures 52 and 53. In
these two figures, the individual air monitoring results obtained
from living area air samples collected in all Canal Area and con-
trol sites sampled are presented in conjunction with the sampling
campaign date.
As can be seen from the results displayed in Figures 52 and
53, some variability in concentration levels was observed across
time. However, most of the variability observed in the sample re-
sults could be accounted for by measurement errors. On the basis
of other statistical analyses conducted with these data, no sig-
nificant functional relationships were observed between the ob-
tained concentration levels and such factors as distance from
Love Canal, wet/dry residences, proximity to a former swale,
diurnal/nocturnal sampling, and sampling campaign. In addition,
the infrequent occurrence and isolation of the (relatively) ex-
treme values present in the data displayed in Figures 52 and 53
should be noted.
The air monitoring data obtained from Love Canal were also
considered in terms of the median concentration values that were
observed. At each site regularly monitored, the median concen-
tration value of all measurements for each substance monitored
was determined. Three typical examples of the results obtained
from this effort are presented in Figures 54 through 56. In
these figures, the living area median concentrations for benzene,
toluene, and 1, 1, 2,2-tetrachloroethylene (respectively) are
displayed for each air site regularly monitored. As can be seen
from the results displayed in Figures 54 through 56, no pattern
of air contamination that was directly related to the migration
of these compounds from Love Canal was found (highest median
concentrations are indicated in the figures).
134
-------
to
Ul
40 -
30 -
O
m <
-
CJ
z
O
o
20
10
SEP.
8
SEP.
16
SEP.
21
SEP.
26
SEP.
30
OCT.
5
OCT.
9
1 ' I' '
OCT.
15
OCT.
20
OCT.
25
OCT.
30
SAMPLE DATE
LEGEND:
H h 11001
D D D 11004
11002
11005
*• 11003
A 11006
Figure 52.
Concentration of Benzene in Living Area Air Samples Collected in
Canal Area Residences (micrograms per cubic meter).
-------
40-
30-
z
o
"J
Ol
20-
U)
ON
o
z
o
o
10-
0-3
SEP.
21
SEP.
26
SEP.
30
OCT. OCT.
5 9
SAMPLE DATE
OCT.
15
OCT.
20
OCT.
25
OCT.
30
LEGEND:
+—*—* 99020
X X X 99022
B—B 99021
©—0- 99023
Figure 53.
Concentration of Benzene in Living Area Air Samples Collected in
Control Area Residences (micrograms per cubic meter).
-------
(SITE 05001}
Figure 54.
Median Concentration of Benzene in Living Area Air
Monitoring Sites Located in the Declaration and Canal
Areas (micrograms per cubic meter).
-------
OJ
03
(SITE 09004)
Figure 55.
Median Concentration of Toluene in Living Area Air Monitoring Sites
Located in the Declaration and Canal Areas (micrograms per cubic meter)
-------
5.3 /zg/m3
(SITE 02053)
5.2 M9/m3
(SITE 04515)
oo
VD
6.
(SITE 08006)
5.
(SITE 09003)
5.1 /ug/m°
(SITE 10005)
Figure 56.
Median Concentration of 1,1,2,2-Tetrachloroethylene in Living Area Air
Monitoring Sites Located in the Declaration and Canal Areas (micrograms
per cubic meter),
-------
Finally, the air monitoring data were considered in terras of
the median concentration values that were observed in each sam-
pling campaign, At each site regularly monitored, the median con-
centration value of all measurements for a compound, for each
compound monitored, was determined according to sampling cam-
paign. Three typical examples of the results obtained from this
effort, incorporating the same compounds just discussed (benzene,
toluene, and 1,1,2,2-tetrachloroethylene), are presented (respec-
tively) in Figures 57 through 59. From a review of the results
presented in Figures 57 through 59, it can be seen that except
for living area air samples collected in the Control Area on
October 20, 1980, the data displayed considerable across-time
consistency. In passing, the reader is reminded that only four
living area control sites were monitored for air contaminants
during each sampling campaign, and greater variability in the
computed median concentration values is to be expected. Further-
more, the relatively minor variability observed in the median
concentrations across time was found to be non-systematic and
attributable mainly to random fluctuations in ambient concentra-
tions of these compounds throughout the general area.
The results from other detailed statistical analyses (not
reported here) conducted on the Love Canal air monitoring data
revealed the following. First, some intraresidence variability
in living area air concentration levels was observed to be asso-
ciated with changes in temperature. Second, the data suggested
that in the Declaration Area some compounds were detected more
frequently in living area samples than in samples collected out-
doors. These compounds included: o-chlorotoluene (26 percent
vs. 15 percent); o-dichlorobenzene (42 percent vs. 10 percent);
p-dichlorobenzene (15 percent vs. 1 percent); and 1,1,2,2-tetra-
chloroethylene (93 percent vs. 82 percent). In addition, the
median living area concentration of 1,1,2,2-tetrachloroethylene
was higher than the outdoor median concentration (4 ^g/mj vs.
trace). Third, in the Declaration Area only one compound, o-
chlorotoluene, was detected more frequently in living area sam-
ples than in basement samples (26 percent vs. 16 percent).
Fourth, there was no indication that residences constructed in
historically "wet" areas exhibited either different percentages
of concentrations above the detection level or different median
concentration levels than non-wet residences. And finally, there
were no indications that residences existing in, or adjacent to,
former swales exhibited either more frequent detections of com-
pounds monitored, or different median concentration levels of
compounds monitored, than non-swale residences.
The three special air monitoring research studies conducted
at Love Canal provided limited evidence of the following addi-
tional results. First, airborne contaminants detected during the
regular indoor air monitoring program were also detected (ordi-
narily at somewhat lower concentration levels) in the ambient
air, and were transported from upwind. Second, highly
140
-------
30—
20-
5
10-
o-i
ry.
OCT.
25
AUG.
22
AUG.
30
SEP.
8
'! » j I I I
SEP.
16
"I"'
SEP.
21
SEP.
26
SEP.
30
''"' 'I'""
OCT.
6
OCT.
9
r? T f i ri
OCT.
15
OCT.
20
OCT.
30
SAMPLE DATE
LEGEND:
X
-+—+- BASEMENT-DECLARATION AREA
X X LIVING-DECLARATION AREA
O
O B LIVING-CONTROL AREA
e— e- OUTDOORS-DECLARATION AREA
MEDIAN-O IMPLIES THAT MEDIAN CONCENTRATION IS BELOW DETECTION
Figure 57,.
Median Concentration of Benzene Observed in Air for Each Sampling
Campaign (micrograms per cubic meter).
-------
to
60~
50
40-
30-
20-
10-
0-
AUG.
22
AUG.
30
'"I"'
SEP.
8
SEP.
16
'••I'"
SEP.
21
SEP.
26
SEP.
30
OCT.
5
OCT
OCT.
15
OCT.
20
OCT.
25
OCT.
30
SAMPLE DATE
LEGEND:
-+—•** BASEMENT-DECLARATION AREA
X X LIVING-DECLARATION AREA
B B O LIVING-CONTROL AREA
•6—©—©• OUTDOORS-DECLARATION AREA
MEDIAN=0 IMPLIES THAT MEDIAN CONCENTRATION IS BELOW DETECTION
Figure 58.
Median Concentration of Toluene Observed in Air for Each Sampling
Campaign (micrograms per cubic meter).
-------
to
100-
7S-
-§0 50
2-
25
I ' ' ' ' ! ' ' ' ' t ' ' ' '"'I '
AUG. AUG. SEP.
22
30
T
SEP. SEP, SEP. SEP. OCT. OCT. OCT. OCT. OCT. OCT.
16 21 26 30 5 9 15 20 25 30
SAMPLE DATE
LEGEND:
•+—*—4- BASEMENT-DECLARATION AREA
XXX LIVING-DECLARATION AREA
ODD LIVING-CONTROL AREA
•O—«—$• OUTDOORS-DECLARATION AREA
MEDIAN=0 IMPLIES THAT MEDIAN CONCENTRATION IS BELOW DETECTION
Figure 59.
Median Concentration of 1,1,2,2-Tetrachloroethylene Observed in Air
for Each Sampling Campaign (mierograms per cubic meter),
-------
contaminated sumps (which were found in only a limited number of
ring 1 residences) could serve as potential contributing sources
of high levels of indoor air pollution. And third, activities
associated with domiciliary occupancy suggested that such activi-
ties could potentially increase air pollution levels.
4.3 EVIDENCE OF OTHER ENVIRONMENTAL CONTAMINATION
As part of the Love Canal multimedia environmental monitoring
program, a number of additional studies were conducted for the
purpose of obtaining information about the likely extent and de-
gree to which residents were directly exposed to environmental
contamination that had migrated from Love Canal. The studies of
potential human exposure conducted included: (1) drinking water
monitoring; (2) monitoring for the uptake of Love Canal-related
contaminants in household foodstuff; (3) environmental radioac-
tivity monitoring; and (4) monitoring for the presence of dioxin
(2,3,7,8-tetrachlorodibenzo-p-dioxin) in environmental samples.
Finally, a limited biological monitoring program was conducted at
Love Canal for the purpose of investigating the potential bio-
logical availability and biological accumulation of Love Canal-
related contaminants in selected locally available biological
species. In Table 12, a summary is presented of the magnitude of
these additional monitoring efforts conducted at Love Canal.
4.3.1 Drinking Water Contamination
As part of the multimedia environmental monitoring program
conducted at Love Canal, an investigation of potential human ex-
posure to toxic substances in drinking water was performed. The
monitoring that was performed entailed collecting samples of
drinking water at a total of 44 sites, involving 42 residences,
and analyzing those samples for the substances identified in
Appendix A of this Volume. Included in the 44 sites were two
separate sites located in the Drinking Water Treatment Plant of
the City of Niagara Falls. The two sites located in the plant
(sites 97013 and 97014) were sampled for the purpose of monitor-
ing raw (untreated) and finished drinking water, respectively.
In Figure 60, the location of drinking water sites sampled in the
general vicinity of Love Canal are presented. In addition to the
sites identified in Figure 60, five control sites were sampled:
site 99010, located on 82nd Street, Niagara Falls; site 99020,
located on Stony Point Road, Grand Island; site 99021, located on
West River Parkway, Grand Island; site 99022, located on Pierce
Road, Niagara Falls; and site 99023, located on Packard Road,
Niagara Falls.
144
-------
X97524
x05001
X97512
X02002
x02004
x01003 x03501
x97514
\
•>nm
j&uu
\l
xl
**s
1
1004
CANAL
AREA
x11
!••«•
x1
002
0£
AW^iJ 1
r-^--1
x06(
x060
x060
x060
1008
»J
I — I
X)5
x070
31
xC
x07C
)7
33
x070
x090l
x 08 003
001 x
xO
xO!
X10004
Figure 60. Drinking Water Sampling Site Codes,
145
-------
TABLE 12. FREQUENCY OF DETECTION OF CONTAMINANTS
IN ADDITIONAL VALIDATED LOVE CANAL SAMPLES
Declaration Area
Control
Canal Area
Deter- Deter- Deter-
minations^ Percent minations Percent minations Percent
Medium/Source
Drinking Water
Foodstuff
Oatmeal
Potatoes
Biota
Crayfish
Dogs
Maple Leaves
Mice
Worms
( Samples )
4,403
(173)
507
(13)
468
(12)
3,169
(31)
308
(23)
150
(15)
3,604
(48)
1,573
(19)
Detect
8.3
11.2
3.4
0.9
62.7
66.0
4.1
2.3
(Samples )
674
(26)
156
(4)
117
(3)
880
(9)
244
(18)
140
(14)
3,601
(45)
616
(5)
Detect
12.9
12.2
3.4
2.2
64.8
64.3
3.6
1.3
(Samples)
710
(25)
117
(3)
78
(2)
0
(0)
0
(0)
80
(8)
553
(7)
528
(6)
Detect
7.6
10.3
4.0
—
—
68.8
4.2
0.9
%otal number of specifically targeted chemicals analyzed for in all
combined validated samples
Note: Inorganic substances represent approximately the following percent
of the determinations in the medium/source identified: drinking
water, 9; dogs, 100; maple leaves, 100; and, mice, 4.
Drinking water samples were collected throughout the course
of the study period, but were obtained only once from each resi-
dential tap sampled. The Niagara Falls Drinking Water Treatment
Plant was sampled twice, in mid-September and mid-October, 1980.
Samples of drinking water were obtained by appropriate proce-
dures, and consisted of composites of tapwater that were collect-
ed over a period of 4 consecutive days at each site sampled? an
additional sample of tapwater was collected on the first day of
sampling for the analysis of targeted volatile compounds. Cri-
teria used for the selection of residential drinking water sam-
pling sites included: (1) sampling at base residences as part of
the multimedia monitoring program? (2) sampling residences in the
Declaration and Canal Areas served by each distribution main? and
(3) randomly (with equal probability) selecting residences for
sampling. In addition, a number of residential taps were sampled
at the request of local residents.
146
-------
The findings of the drinking water monitoring program may be
stated concisely. First, no evidence was found (at the limits of
detection employed in this study) that the drinking water samples
analyzed were directly contaminated by the infiltration of con-
taminants from Love Canal into the water distribution mains sam-
pled. Second, organic compounds primarily detected in the drink-
ing water were trihalomethanes, which are typically formed in
drinking water as a result of the bacteria-killing chlorination
treatment process. The concentration levels of the trihalo-
methanes found in the drinking water were less than, or compar-
able to, the levels commonly reported elsewhere. (See appendix B
of this Volume). Third, the concentration levels of substances
detected in drinking water samples satisfied the existing EPA Na-
tional Interim Primary Drinking Water Regulations, and the Recom-
mended National Secondary Drinking Water Regulations. (See Table
B-ll in Appendix B of this Volume). In comparing the obtained
drinking water concentration levels of the results presented in
Appendix B, note that 1 part per billion (ppb) equals 0.001 part
per million (ppm). Finally, the observed variability in concen-
tration levels of substances detected in drinking water samples
could not be distinguished from either measurement error varia-
tion or from the day-to-day variation in finished water quality
normally observed at treatment plants.
In Figure 61, one typical example of the findings obtained
from the drinking water monitoring program is presented. The
compound presented in Figure 61 is the trihalomethane, chloro-
form. As can be seen, no pattern of drinking water contamination
was found in the Declaration Area. Additional figures are in-
cluded in Volume III.
4.3.2 Food Contamination
One of the supplementary, limited monitoring studies conduct-
ed at Love Canal involved the purposeful introduction of food-
stuff into a select number of air monitoring residences. The ob-
jective of this investigation was to determine whether or not the
foods introduced accumulated airborne contaminants that were
present in the residence by virtue of direct migration from the
former canal. It was suspected that if accumulation was found to
occur, then residents might also be subjected to incremental
chemical insult (assuming sufficient accumulation occurred) from
the ingestion of such foods.
The items selected for introduction to a limited number of
residences were oatmeal and (not locally grown) potatoes. These
foods were chosen due to their common usage and because they were
thought to be relatively efficient accumulators of airborne con-
taminants. Quantities of these foods were acquired and intro-
duced to the basements of certain air monitoring residences for a
period of approximately 30 days, and analyzed subsequently for
147
-------
x18
Legend:
T-Trace
B—Below Detection
N—No Analysis
Figure 61.
Drinking Water Sampling Sites,
Chloroform, Maximum Concentrations
(micrograms per liter, ppb).
148
-------
the volatile compounds listed in Table A-l of Appendix A to this
Volume. Those sites in the general Love Canal area in which sam-
ples of oatmeal and potatoes were stored are identified (where
possible) in Figure 62.
In addition to the sites identified in Figure 62, the follow-
ing control sites were sampled (site locations were previously
identified): sites 99020, 99022, and 99023 for both oatmeal and
potatoes r and site 99021 for oatmeal only. A total of 18 sites
were used for oatmeal monitoring and 16 sites were used for po-
tato monitoring. Those residences in which samples of oatmeal
and potatoes were introduced included base residences and other
randomly selected air monitoring sites.
The results obtained from the analysis of oatmeal and potato
samples suggested that these foods may potentially accumulate
airborne contaminants. It should be noted, however, that the few
compounds which were detected in food samples analyzed after
storage were present typically at very low trace concentrations
(although they were not detected in one sample analyzed prior to
storage). The degree to which these findings represent false-
positive determinations is not known. Details on the compounds
found in foodstuff field samples may be found in Volumes II and
III.
The following points should be considered when attempting to
interpret the meaning of the results obtained from the oatmeal
and potatoes monitoring program. First, only a few of the com-
pounds monitored were uniquely detected after storage. Second,
those compounds uniquely detected after storage were typically
observed at very low trace concentrations. Third, because no air
contamination was found that could be directly attributed to con-
taminants migrating from the former canal, no significance can be
attached to the results of the oatmeal and potatoes monitoring
program findings. And finally, because no samples were stored
for an identical length of time in a controlled, contaminant-free
environment and then subsequently analyzed, no attribution of the
source of observed compounds found in stored field samples can be
unequivocally made.
4.3.3 Radioactive Contamination
The multimedia environmental monitoring program also included
an extensive investigation of the potential presence of radioac-
tive contamination in the general Love Canal area. In order to
characterize the extent and degree of radionuclides present in
the environment, many of the same sites sampled for water, soil,
and sediment were sampled simultaneously for the determination of
radioactive contaminants. The following numbers of sites were
sampled to determine the radionuclides presents 106 soil sampling
sites; 36 sump water sampling sites? the one sanitary sewer sam-
pling site; 20 storm sewer water and 11 storm sewer sediment sam-
pling sites; 2 surface water and 2 stream sediment sampling
149
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X07002
X07501
X07001
08001 x09001
X ! !
Figure 62. Oatmeal and Potatoes Sampling Site Codes
150
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sites? and 10 drinking water sampling sites. Due to the large
percentage of sites sampled in each of the medium/source/location
categories identified, and because all sampling sites were iden-
tified in previous figures, no additional site-specific figures
showing the locations sampled for radioactive contaminants are
presented.
All samples collected for the determination of radioactive
contamination were analyzed for gamma-emitting radionuclides by
high resolution gamma spectroscopy. The particular system em-
ployed allowed for the detection of all gamma-emitting radionu-
clides present in a sample in quantities significantly above
background levels. In Table 13 the minimum detection levels
(based on a 350-gram sample counted for 30 minutes and the aver-
age efficiency of the detectors used) are reported for those
gamma-emitting radionuclides detected in Love Canal samples.
Drinking water samples were also analyzed for tritium (the
radioactive form of hydrogen), in addition to the analysis for
gamma-emitting radionuclides. The standard method for tritium
analysis, liquid scintillation counting of beta emissions, was
employed. The minimum detection level of tritium in drinking
water, corresponding to this method, was approximately 300 pico-
curies per liter (300 pCi/liter). The EPA drinking water stan-
dard for tritium is 20,000 pCi/liter.
TABLE 13. MINIMUM DETECTION LEVELS FOR PARTICULAR
GAMMA-EMITTING RADIONUCLIDES
Radionuclide Water Samples Soil/Sediment Samples
Potassium^ 2.2 grams per liter 0.0019 grams per gram
Radium-226 50 picocuries per liter 0.04 picocuries per gram
Radium-228 200 picocuries per liter 0.2 picocuries per gram
"Approximately 0.0118 percent of all natural potassium consists
of the radioactive isotope potassium-40.
Notes No americium-241 was detected in any samples analyzed.
Because of the concerns expressed by some residents about
its potential presence, its minimum detection level is re-
ported here: in water, 280 picocuries per liter; and in
soil/sediment, 0.025 picocuries per gram.
In general, the results obtained from monitoring for environ-
mental radioactive contamination in the Declaration and Canal
Areas revealed no evidence of radioactive contamination present
at, or having migrated from, Love Canal. Those radionuclides
found in soil consisted of the naturally occurring potassium-40
and the (so-called) daughter products of the radium-226 and the
151
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thorium-232 decay chains. Three soil samples were also found to
contain low levels of cesium-137, comparable in concentration to
the levels of cesium-137 attributed to worldwide fallout. Radio-
analyses of all water samples collected, including drinking
water, revealed that no gamma-emitting radionuclides were present
above background levels. Analyses of the drinking water samples
for tritium yielded a maximum concentration of approximately
1,800 picocuries per liter, a value well below the current EPA
drinking water maximum contaminant level (20,000 pCi per liter).
Storm sewer sediment samples collected from the Canal Area
were found to contain low levels of potassium-40, corresponding
to 5 to 8 milligrams of total potassium per gram of sediment.
All Canal Area storm sewer sediment samples also contained low
levels of cesium-137 (0.014 to 0.79 pCi per gram). These levels
are consistent with values found in other parts of the country,
and are attributable to worldwide fallout. Radium-226 in storm
sewer sediment from the Canal Area varied in concentration from
0.39 to 0.94 pCi per gram. All of the storm sewer sediment sam-
ples from the Canal Area contained daughter products of thorium-
232. Assuming equilibrium of the daughter products with the
thorium-232, the concentration ranged from 0.23 to 0.36 pCi of
thorium-232 per gram of sediment.
Storm sewer sediment samples collected in the Declaration
Area contained from 2 to 27 milligrams of potassium per gram of
sediment. A total of 24 samples were found to contain cesium-137
at concentrations ranging from 0.084 to 0.97 pCi per gram, com-
parable once again to worldwide fallout levels. Radium-226 in
storm sewer sediment samples from the Declaration Area varied in
concentration from 0.20 to 6.6 pCi per gram; only three of the
samples had concentrations of radium-226 greater than 1 pCi per
gram (1.6, 2.2, and 6.6 pCi per gram). In addition, a number of
storm sewer sediment samples from the Declaration Area contained
the daughter products of thorium-232, at levels that indicated a
thorium-232 concentration ranging from 0.22 to 1.9 pCi of
thorium-232 per gram of sediment.
Finally, stream sediment samples collected from the Declara-
tion Area were found to contain only trace quantities of natural-
ly occurring potassium-40. Samples of stream sediment collected
from a control site revealed similar concentrations of potassium-
40, and also contained low levels of radium-226 (0.3 pCi per
gram) and thorium-232 (0.1 pCi per gram).
4.3.4 Biological Monitoring of Contaminants
A limited program of biological monitoring, involving select-
ed native biological species, was conducted for the purpose of
investigating the potential biological availability and biologi-
cal accumulation of contaminants that may have migrated from Love
Canal. It should be made clear that the biological monitoring
152
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program was neither designed nor intended to provide insight into
the health or ecological effects of those contaminants that might
be found in biota. Furthermore, the monitoring program was not
intended, and made no attempt, to determine the behavior of any
chemicals found in the biological species investigated, to deter-
mine the kinetics of biological uptake, or to determine the im-
pact of the chemicals monitored on the species considered. Rath-
er, the biological monitoring program was intended to provide
limited, suggestive indication of the accumulation of contami-
nants in biological systems, thereby potentially increasing the
sensitivity of the entire monitoring program to the presence of
environmental contaminants that may have migrated from the former
canal.
The local species selected for monitoring purposes were cray-
fish (Orconectes propinquis), domestic dogs (Canis familiaris),
field mice (Microtus pennsylvanicus), silver maple tree leaves
(Acer saccharinum), and worms (Lumbricus sp.). In Table 14, the
scope of the biologica1 monitoring program is presented. In Fig-
ure 63 the locations of biota sampling sites in the Declaration
and Canal Areas are presented.
The procedures used to collect samples of the biological
species monitored were as follows. Crayfish were obtained by
seining approximately 100 meters of Black Creek and Bergholtz
Creek, in the general vicinity of local storm sewer outfalls.
TABLE 14. SCOPE OF THE BIOLOGICAL MONITORING PROGRAM
Number of Samples
(Number of Sites)
Targeted
Substances
Specy
Crayfish
Dogs
Mice
Mice
Silver
Maple
Worms
Sample
10 grams
composite;
whole body
2 grams of
neck hair
whole car-
cass
body hair
10 grams
composite;
leaves
10 grams
composite ?
whole body
Declaration
31
(1)
23
(20)
36
(5)
12
(5)
15
(14)
19
(4)
Control
9
(1)
18
(15)
33
(2)
12
(2)
14
(ID
5
(3)
Canal
—
__
—
—
5
(2)
2
(2)
8
(6)
6
(2)
Monitored
Organics
Inorganics
Organics
Inorganics
Inorganics
Organics
Note: Targeted substances monitored are identified in Table
A-l of Appendix A in this Volume. Dashes signify not
applicable.
153
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S05036
S05037 S05035
d05021
n
:17 CI05016
m07505
10052
is m10055
w
10003
c -CRAYFISH
d - DOG
m-MICE
s -SILVER MAPLE
w-WO RMS
s10053
Figure 63. Biota Sampling Site Codes
154
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Crayfish were obtained similarly from the control site 99035, lo-
cated north of Niagara University in Fish Creek. Subsequent to
capture, the crayfish were stored in a holding tank (filled with
the local creek water from which they were taken) for a fasting
period of 48 hours, in order to allow purging of the digestive
tract. After the holding period expired, the whole bodies of two
or three crayfish were homogenized to form a composite sample of
approximately 10 grams, which was necessary for analysis pur-
poses .
Samples of dog hair were obtained from mature domestic dogs
(household pets) , that were raised in the Declaration Area and
provided voluntarily by local residents. Approximately 2 grams
of hair were taken from each dog by clipping along the side of
the neck.
Field mice were captured by means of live traps placed at the
locations indicated in Figure 63, and at control sites 99035 (lo-
cated north of Niagara University along Fish Creek) and 99071
(located near the intersection of 66th Street and Frontier Avenue
in Niagara Falls). Shortly after capture, the obtained specimens
were sacrificed by cervical dislocation. Samples of hair were
obtained by shaving each mouse of all body hair, and forming com-
posites of body hair from three mice captured in the same general
location. After shaving, each mouse was skinned and the legs and
tail were removed. The carcass was then eviscerated and the re-
mainder homogenized to form a sample that was submitted for
analysis.
The leaves from silver maple trees were collected in the
general area of the sites identified in Figure 63 and at control
sites. Samples were formed by compositing 10 outer leaves from
each of 10 silver maple trees located at each site. Composite
samples that were formed consisted of at least 10 grams of dry
leaves.
Finally, worms were collected from the sites identified in
Figure 63 and from the control sites 99008 (located on Frontier
Avenue, Niagara Falls), 99020 (located on Stony Point Road, Grand
Island), and 99021 (located on West River Parkway, Grand Island).
Prior to sampling, each site was watered (if necessary) in order
to saturate the surface soil. One-meter square plots were then
dug to a depth of 15 centimeters and the unearthed worms were
collected. After collection, the worms were placed in moist
cornmeal for 24 hours to allow purging of the digestive tract.
Next, 10-gram composite samples of worms obtained from each plot
were homogenized prior to analysis.
The results from the biological monitoring program were found
to be of limited value. Because the results obtained did not
demonstrate the biological uptake of contaminants from the former
canal (that is, the findings conformed with the results of the
155
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environmental monitoring program), they will not be discussed in
detail "here. The interested reader is instead referred to Vol-
umes II and III of this report for more specific information.
4.3.5 Dioxin (2,3,7,8-TCDD)
By intent, the results of specific monitoring for tetrachlor-
inated dibenzo-p-dioxins (TCDDs), particularly the 2,3,7,8-TCDD
isomer, in environmental samples collected in the vicinity of
Love Canal were reserved for unified presentation. The motiva-
tion for a separate discussion of the sampling, analytical, and
quality assurance procedures and results for TCDDs analyses
stemmed, in part, from the high toxicity of the 2,3,7,8-TCDD
isomer and, in part, from the expressed concerns of local resi-
dents regarding potential sources of human exposure.
As part of the multimedia environmental monitoring program
conducted at Love Canal, a number of samples were analyzed by
high resolution gas chromatography/high resolution mass spec-
trometry (HRGC/HRMS) for the determination of 2, 3, 7, 8-TCDD. In
Figure 64, the locations of sites monitored for 2, 3, 7,8-TCDD are
given, and are identified by medium and source. As with many
other environmental samples collected at Love Canal, the selec-
tion of 2,3,7,8-TCDD monitoring sites was directed intentionally
towards known or suspected transport pathways. For example, the
limited results from previous investigations of TCDDs at Love
Canal by NYS were used partially to aid in the selection of
2, 3, 7, 8-TCDD sampling sites .
All samples collected for the determination of 2,3,7,8-TCDD
were analyzed by Wright State University (WSU) under the direc-
tion of the EPA Health Effects Research Laboratory, Research
Triangle Park, North Carolina (HERL-RTP). Air samples were col-
lected on polyurethane foam plugs and were extracted with ben-
zene. Water, soil, and sediment samples were collected as de-
scribed previously and were extracted using petroleum ether and
agitation. Primary extracts were subjected, as necessary, to
extensive additional purification prior to analysis. The labeled
internal standard 3*7ci^-2, 3, 7,8-TCDD was added to all samples
before primary extraction. Additional details concerning the
analytical methods used for 2,3,7,8-TCDD determinations may be
found in G. F. Van Ness, et al., Chemosphere, Vol. 9 (1980),
553-563, and R. L. Harless, et al., Analytical Chemistry, Vol.
52, No. 8 (1980), 1239-1245.
The limit of detection for the methodology was ordinarily in
the range of 1 to 20 nanograms per "kilogram or nanograms per lit-
er (parts per trillion -- ppt), and varied according to sample
medium and sample source. For example, samples containing a rel-
atively high organic content (such as aquatic sediment samples)
had an associated limit of detection near the upper end of the
range, while samples free of organic interferences had a limit of
detection near the lower end of the range.
156
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&07501
11032 08015 09017
11021
AIR
GROUND WATER
LEACHATE TREATMENT FACILITY
STORM SEWER SEDIMENT
STREAM SEDIMENT
SUMPS
SOILS
10033
• 97543
Figure 64. Sampling Site Codes for Dioxin
(2,3,7,8-TCDD).
157
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Analytical performance of WSU was evaluated regularly during
the Love Canal project. Performance evaluation samples were
prepared by HERL-RTP by adding known amounts of 2,3,7,8-TCDD to
specially obtained samples of soil. These samples were submitted
to WSU, along with actual Love Canal field samples, in a manner
that precluded their identification as performance evaluation
samples. The performance evaluation samples prepared contained
either no added analyte, 60 ppt of 2,3,7,8-TCDD, or 120 ppt of
2, 3, 7,8-TCDD. On the basis of these samples the performance of
WSU for 2,3,7,8-TCDD determinations was judged, in all instances,
acceptable.
All analytical determinations for 2,3,7,8-TCDD by WSU were
validated by HERL-RTP. Every extract containing a positive de-
termination of TCDDs was divided by WSU, and a portion was sent
to HERL-RTP for confirmation and isomer identification on a
different HRGC/HRMS system. All postive determinations of
2,3,7,8-TCDD were validated in this fashion, and all samples
collected for the analysis of TCDDs were validated.
The recovery 2,3,7,8-TCDD from the performance evaluation
soil samples varied from 32 to 77 percent. These results, how-
ever, are not considered valid indicators of the accuracy of the
soil and sediment methodology. As is pointed out in Appendix D,
in the section entitled "Limits of Detection/Quantitation," it is
very difficult to add a known amount of an analyte (or analytes)
to a soil/sediment sample and simulate the natural sorption or
uptake processes. Therefore, while the results from the perfor-
mance evaluation samples cannot be used to estimate the accuracy
of the method, they do generally confirm the method limit of de-
tection .
In addition, one Love Canal water sample that contained no
detectable amount of 2,3,7,8-TCDD was spiked by WSU with 91 ppt
of 2,3,7,8-TCDD. This water sample was sent to HERL-RTP (in
blind fashion) for extraction and analysis. The recovery of
2,3,7,8-TCDD from this water sample by HERL-RTP was 71 percent,
which is an indicator of the accuracy of the method for 2,3,7,8-
TCDD determinations in water samples.
The precision of the methodology for 2,3,7,8-TCDD determina-
tions is indicated by the positive results from the measurement
of duplicate Love Canal field samples presented in Table 15. When
expressed in terms of percent relative range (the difference be-
tween duplicate measurements as a percentage of the mean of the
two measurements), the precision of the method was 5.2 percent
and 26 percent for the two duplicates with hundreds of parts per
billion concentrations, and 87 percent for the one duplicate with
parts per trillion concentrations.
The results obtained from the special 2,3,7,8-TCDD monitoring
program were as follows. The presence of 2,3,7,8-TCDD in Love
158
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TABLE 15. RESULTS OF STORM SEWER SEDIMENT DETERMINATIONS
FOR 2,3,7,8-TCDD
(micrograms per kilogram)
Site
Location
2,3,7,8-TCDD
Concentration (ppb)
11030 97th Street and Read Avenue
04508 97th Street and Colvin Boulevard*
02501 96th Street and Colvin Boulevard*
04506 96th Street and Greenwald Avenue*
329
672 and 638*
5.39
170
04507
02032
11031
11033
10032
10033
10035
11032
08015
09017
06017
07018
03511
03510
01028
03526
02031
97th Street and Greenwald Avenue
96th Street, near Apt. 620 in Court 2
97th Street and Wheatfield Avenue1"
97th Street and Frontier Avenue*
100th Street and Frontier Avenue*
102nd Street and Frontier Avenue*
Buffalo Avenue near 10108 Buffalo*
99th Street and Wheatfield Avenue*
101st Street and Wheatfield Avenue*
102nd Street and Wheatfield Avenue*
100th Street and Colvin Boulevard*
101st Street and Colvin Boulevard*
Frontier Avenue between 93rd and
96th Streets
93rd Street and Frontier Avenue
Frontier Avenue between 92nd and
93rd Streets
93rd Street and Read Avenue
93rd Street and Colvin Boulevard
B
B
199
393 and 303*
0.2 and B*
B and B*
B
0.2
0.4
B
0.054
B
B and B*-
B
B and B*
B
0.165 and 0.419*
*Storm sewer line turning point or junction
*Duplicate analyses performed
B: Below detection
Note: As best as possible, storm sewer sites are organized by
sewer line and presented according to sequential waterflow
direction originating at those sites located closest to
the midpoint of Love Canal. (See Figure 12).
159
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Canal was determined from the analysis of two leachate samples
collected in the Leachate Treatment Facility (site 11076). The
results of the analyses conducted on the solution phase samples
of leachate revealed a concentration of 1.56 micrograms per liter
(ppb) in the untreated influent sample, and below detection level
results (approximately 5 to 10 nanograms per liter) for the
treated effluent sample.
The presence of 2, 3, 7, 8-TCDD was not detected in any of the
ground-water samples analyzed. And, no 2, 3,7,8-TCDD was detected
in any of the soil samples analyzed. Note, however, that no soil
samples were collected directly in the known sand lens on the
western side of Love Canal, where 2, 3, 7, 8-TCDD had been found
previously by NYS DOH.
The only sumps found to contain measurable amounts of
2,3,7,8-TCDD were located in ring 1 residences in the Canal Area.
The sumps found to contain 2,3,1, 8-TCDD were also noted previous-
ly as containing high levels of contamination, with numerous
other organic compounds present. In particular, the sump sediment
sample collected from site 11072 (located at 771 97th Street), a
residence identified previously as collinear with the known sand
lens on the western side of Love Canal, had a high concentration
of 9,570 ppb of 2, 3, 7, 8-TCDD present. In addition, the two sumps
located in the residence at site 11021 (476 99th Street) had
2,3,7, 8—TCDD present at concentrations of 0.5 ppb and 0.6 ppb.
The sample of sump sediment obtained from site 11073 (703 97th
Street) contained no measurable amount of 2, 3, 7, 8-TCDD,
The presence of 2,3,7,8-TCDD was detected in a number of
storm sewer sediment samples collected from throughout the gener-
al Love Canal area. The results obtained are summarized in Table
15. Note that in Table 15 an attempt was made to group sampling
sites by storm sewer line, and to list sites by waterflow direc-
tion starting at Love Canal. As can be seen from the results pre-
sented in Table 15, decreasing concentrations of 2,3,7,8-TCDD
were found in certain storm sewer lines as distance from the for-
mer canal increased. In particular, starting with the storm sew-
er turning points on 97th Street and on 99th Street, decreasing
concentration-s of 2, 3, 7,8-TCDD were found in the storm sewer
lines heading in the direction of the 96th Street outfall, the
outfall in Black Creek between 101st and 102nd Streets, and the
102nd Street outfall. (See Figure 12).
These findings strongly suggest that the transport of sedi-
ment by waterflow served as the likely mechanism of 2, 3, 7, 8-TCDD
movement through the storm sewer lines sampled. The fact that
2,3,7,8-TCDD has very low solubility in water and very high sorp-
tion properties on sediment, tends to support this hypothesis.
The stream sediment samples analyzed for 2, 3, 7, 8-TCDD re-
vealed that 2, 3, 7, 8-TCDD had likely been transported through the
160
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storm sewer lines into the creeks and river sampled. At site
04014, located in Black Creek near 98th Street, 0.075 ppb of
2, 3, 7, 8-TCDD was detected. Further west in Black Creek, at site
04015, located near the storm sewer outfall, 37.4 ppb of 2,3,7,8-
TCDD was detected. While at site 04016, located in Bergholtz
Creek near its junction with Black Creek, 1.32 ppb of 2,3,7,8-
TCDD was found. Further downstream in Bergholtz Creek at site
97526, located west of 93rd Street, the presence of 2, 3, 7, 8-TCDD
was not detected. Also sampled was site 97543, located in the
Niagara River near the 102nd Street storm sewer outfall. Sedi-
ment from this site was analyzed in triplicate and yielded con-
centrations of 0.1, 0.06, and 0.02 ppb of 2, 3, 7, 8-TCDD. Because
of the proximity of site 97543 to the 102nd Street landfill, and
the failure to detect 2, 3, 7,8-TCDD in the storm sewer site sam-
pled closest to the outfall (site 10035), the source of the
2, 3, 7,8-TCDD present in the Niagara River could not be clearly
identified.
Finally, no 2,3, 7,8-TCDD was detected in any of the air
samples analyzed.
To reiterate, it was determined that 2,3,7,8-TCDD was present
in the untreated leachate, in the sumps of certain ring 1 resi-
dences, in the sediment of storm sewers emanating from near the
former canal, and in the sediment of local creeks and the Niagara
River sampled in the vicinity of outfalls of storm sewer lines
that originated * near Love Canal. These results for Love Canal-
related 2,3,7,8-TCDD environmental contamination are in confor-
mity with the findings presented earlier, and are also in agree-
ment with the less comprehensive results reported by NYS DOH in
1980,
161
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CHAPTER 5
SUMMARY AND CONCLUSIONS
The EPA multimedia environmental monitoring program conducted
at Love Canal provided a substantial amount of information on the
extent and degree of environmental contamination in the Declara-
tion Area that resulted directly from the migration of contami-
nants from the former canal. In general, the monitoring data re-
vealed that except for residual contamination in certain local
storm sewer lines and portions of creeks located near the out-
falls of those storm sewers, the occurrence and concentration
levels of chemicals found in the Declaration Area (in each media
monitored) were comparable to those found at nearby control
sites. The monitoring data also revealed that contamination that
had most likely migrated directly from Love Canal into residen-
tial areas was confined to relatively localized portions of ring
1 in the Canal Area (that is, near certain unoccupied houses lo-
cated adjacent to the former canal). In addition, comparative
data from other locations in the United States (presented in
Appendix B of this Volume) revealed that the observed occurrence
and concentration levels of .those chemicals monitored in the
residential portions of the Declaration Area and elsewhere were
comparable. Furthermore, comparisons of the concentration levels
of environmental contaminants found in the residential portions
of the Declaration Area with existing EPA standards revealed that
no environmental standards were violated.
A review of all of the environmental monitoring data collect-
ed at Love Canal also revealed that no evidence was obtained
which demonstrated that residential portions of the Declaration
Area exhibited measurable environmental contamination that was
directly attributable to the presence of contaminants that had
migrated from the former canal. In addition, it is unlikely that
undetected Love Canal-related contamination exists in the resi-
dential portions of the Declaration Area, because the targeted
substances monitored and the sampling locations selected for
monitoring purposes were intentionally directed (based on the
best available evidence) to maximize the probability of detecting
contaminants that had migrated from the former canal.
162
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The absence of Love Canal-related environmental contamination
in the Declaration Area, other than that which was mentioned pre-
viously, conformed with the results and implications of the
hydrogeologic investigations conducted in the general Love Canal
area. Specifically, the well-defined multimedia pattern of
environmental contamination found in shallow system ground-water
samples, in soil samples, and in sump samples collected at cer-
tain locations in ring 1 of the Canal Area, was in full agreement
with (and corroborated) the hydrogeologic program results.
The following points highlight the major findings of the EPA
multimedia environmental monitoring program conducted at Love
Canal.
• The hydrogeologic program results demonstrated that there
is little potential for migration of contaminants from Love
Canal into the Declaration Area. These findings conformed
fully with the results of the multimedia environmental
monitoring program. Furthermore, the close correspondence
of the multimedia monitoring data to the implications of
the geological and hydrological characteristics of the
site minimized the likelihood that potential limitations
inherent in the state-of-the-art analytical methods used
during the study resulted in artifactual or fallacious con-
clusions regarding the extent and degree of environmental
contamination at Love Canal.
• The results from the hydrogeologic program suggested that
the barrier drain system, which was installed around the
perimeter of Love Canal in 1978 and 1979, is working as de-
signed. In particular, the outward migration of contami-
nants through more permeable overburden soil has been con-
tained, and the movement of nearby shallow system ground
water is towards the drain. Consequently, contaminated
shallow system ground water beyond the barrier drain will
be drawn towards Love Canal, intercepted by the barrier
drain system, and decontaminated in the Leachate Treatment
Facility. Previously reported EPA testing of the effec-
tiveness of the Leachate Treatment Facility demonstrated an
operating efficiency of greater than 99 percent removal of
all monitored organic compounds in the influent leachate.
Discharged liquids from the facility are transported
through the sanitary sewer system to the City of Niagara
Falls wastewater treatment plant for additional treatment.
• Except for some apparently isolated pockets of shallow sys-
tem ground-water contamination located immediately adjacent
to the former canal, no general pattern of contamination
163
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was found in the shallow system. Furthermore, no signifi-
cant shallow system ground-water contamination attributable
directly to migration from Love Canal was found outside of
ring 1 in the Canal Area.
* Low level, widespread contamination was observed throughout
the bedrock aquifer. However, ground-water samples from
the bedrock aquifer located in the Lockport Dolomite did
not reveal a pattern of contamination that had migrated
directly from Love Canal.
* No Love Canal-related patterns of contamination were found
in soil samples collected in the Declaration Area. Patterns
of soil contamination attributable to contaminants having
migrated from Love Canal were found in ring 1 of the Canal
Area, and were associated with known or suspected preferen-
tial transport pathways in the soil, and with the occur-
rence of shallow system ground-water contamination.
* No evidence of Love Canal-related contamination that had
migrated preferentially through former swales into the Dec-
laration Area was found, nor were "wet" area residences
found to have higher concentrations of contamination than
"dry" residences.
* Evidence of residual contamination that had most likely
migrated from Love Canal was present in sump samples col-
lected in a few residences located immediately adjacent to
the former canal (that is, within ring 1).
• Evidence of residual contamination that had most likely
migrated from Love Canal was found in those storm sewer
lines which originated near Love Canal in the Canal Area.
* Evidence of residual contamination that had most likely
migrated from Love Canal was present in the sediments of
certain creeks and rivers sampled near to those storm sewer
outfalls of sewer lines originating near the former canal.
* Results from monitoring activities in the residential por-
tions of the Declaration Area revealed that the contamina-
tion present was comparable to that at the control sites,
to concentrations typically found in the ambient environ-
ment, and to concentrations found in other urban locations.
In general, no environmental contamination that was direct-
ly attributable to the migration of contaminants from Love
Canal was found in the Declaration Area (outside of the
previously mentioned storm sewer lines and creeks).
164
-------
Finally, a review of the results from the entire Love Canal
environmental monitoring study revealed that: (I) except for
contamination present in sediments of certain storm sewers and of
certain local surface waters, the extent and degree of environ-
mental contamination in the area encompassed by the emergency
declaration order of May 21, 1980 were not attributable to Love
Canal; (2) the short-term implications of ground-water contamina-
tion are that a continued effective operation of the barrier
drain system surrounding Love Canal will contain the lateral mi-
gration of contaminants through the overburden, and the long-term
implications are that little likelihood exists for distant
ground-water transport of contaminants present in the Canal Area;
and (3) a review of all of the monitoring data revealed that
there was no compelling evidence that the environmental quality
of the Declaration Area was significantly different from control
sites or other areas throughout the United States for which moni-
toring data are available.
165
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APPENDIX A
LISTS OF SUBSTANCES MONITORED AT LOVE CANAL
The following two tables contain lists of substances that
were routinely determined in samples collected during the EPA
Love Canal multimedia environmental monitoring program. Table A-l
contains a list of targeted organic and inorganic substances that
were determined in water, soil, sediment, and biological samples.
In Table A-2, a list is presented of targeted organic and inor-
ganic substances that were determined in air samples.
TABLE A-l.
SUBSTANCES MONITORED IN LOVE CANAL
WATER/SOIL/SEDIMENT/BIOTA SAMPLES
Volatiles-Method 624 Analytes
(Medium: Water/Soil/Sediment/Biota)
Methylene chloride
Chloromethane
1,1-Dichloroethene
Bromomethane
1,1-Dichloroethane
Vinyl chloride
cis-1,2-Dichloroethene
Chloroethane
trans-1,2-Dichloroethene
Trichlorofluoromethane
Chloroform
1,2-Dichloroethane
1,2-Dichloroethene
1,1,1-Trichloroethane
Carbon tetrachloride
Bromochloromethane
Bromodichloromethane
2,3-Dichloropropene
1,2-Dichloropropane
Trichloroethene
trans-1,3-Dichloropropene
Benzene
Acrolein
Acrylonitrile
Dibromochloromethane
1,1,2-Trichloroethane
Bromoform
1,1,2,2-Tetrachloroethane
Benzyl chloride
o-Xylene
m-Xylene
p-Xylene
Tetrachloroethene
Toluene
2-Chlorotoluene
3-Chlorotoluene
4-Chlorotoluene
Chlorobenzene
Ethyl benzene
1,2-Dibromoethane
(continued)
166
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TABLE A-l (continued)
Phenols and Base/Neutrals-Method 625 Analytes
(Mediums Water/Soil/Sediment/Biota)
2-Chlorophenol
3-Chlorophenol
4-Chlorpphenol
2-Nitrophenol
Phenol
2,4-Dimethylphenol
2,4-Dichlorophenol
2,3,5-Trichlorophenol
2,4,6-Trichlorophenol
4-Chloro-3-methylphenol
2,4-Dinitrophenol
2-Methyl-4,6-dinitrophenol
Pentachlorophenol
4-Nitrophenol
Hexachloroethane
1,4-Dichlorobenzene
1,3-Dichlorobenzene
1,2-Dichlorobenzene
Bis(2-chloroethyl)ether
Bis(2-chloroisopropyl)ether
N-nitrosodi-n-propylaraine
Hexachlorobutadiene
1,2,3~Triehlorobenzene
N-nitrosodimethylamine
1,2,4-Trichlorobenzene
1,3,5-Trichlorobenzene
Nitrobenzene
Naphthalene
Isophorone
Bis(2-chloroethoxy)methane
Hexachlorocyclopentadiene
(C-56)
2-Chloronaphthalene
Acenaphthylene
Acenaphthene
DimethyIphthalate
2,6-Dinitrotoluene
Fluorene
1,2-Diphenylhydrazine
4-Chlorophenylphenylether
2,4-Dinitrotoluene
2,4-Dichlorotoluene
Diethylphthalate
N-nitrosodiphenylamine
Hexachlorobenzene
4-Bromophenylphenylether
Phenanthrene
Anthracene
Di-n-butyl phtalate
Fluoranthene
Pyrene
Benzidine
ButylbenzyIphthalate
Di(2-ethylhexyl)phthalate
Chrysene
Di-n-octyIphthalate
Benzo(a)anthracene
Benzo(k)fluoranthene
Benzo(b)fluoranthene
Benzo{a)pyrene
3,3-Dichlorobenzidine
Indeno(l,2,3-dc)pyrene
Dibenzo(a,h5anthracene
Benzo(g,h,i)perylene
Pentachloronitrobenzene
2,4,6-Trichloroaniline
4-Chlorobenzotrifluoride
(Trifluoro-p-chlorotoluene)
1,2,3,4—Tetrachlorobenzene
1,2,4,5-Tetrachlorobenzene
Tetrachlorotoluenes
(18 position isomers—ring
and methyl substitution)
(continued)
167
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TABLE A-l (continued)
Aroclors (PCBs) and Pesticides-Methods 608 and 625 Analytes
{Mediums Water/Soil/Sediment/Biota)
a-BHC
0-BHC
6-BHC
T-BHC (Lindane)
Heptaehlor
Aldrin
Mirex
Endosulfan I
Heptachlor epoxide
DDE
Endrin
Endosulfan II
Dieldrin
Endosulfan sulfate
ODD
Chlordane
DDT
Toxaphene
Aroclor 1221
Aroclor 1254
Aroclor 1016
Aroclor 1232
Aroclor 1242
Aroclor 1248
Aroclor 1260
Inorganics
(Medium: Water/Soil/Sediment/Biota)
and
Fluoride and Nitrate
(Medium: Water)
Antimony
Arsenic
Barium
Beryllium
Cadmium
Chromium
Copper
Lead
Mercury
Nickel
Selenium
Silver
Thallium
Zinc
Fluoride
Nitrate
Note: 2,3,7,8-Tetrachlorodibenzo-p-dioxin was quantitatively
determined in a select number of samples.
168
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TABLE A-2.
SUBSTANCES MONITORED IN LOVE CANAL
AIR SAMPLES
Volatiles
(Source: TENAX)
Quantitative Analysis
Qualitative Analysis
Benzene
Carbon tetrachloride
Chlorobenzene
o-Chlorotoluene
p-Chlorotoluene
1,2-Dibromoethane
o-Dichlorobenzene
p-Dichlorobenzene
1,1,2,2-Tetrachloroethylene
Toluene
Chloroform
1,2-Dichloroethane
2,4-Dichlorotoluene
o-Chlorobenzaldehyde
p-Chlorobenzaldehyde
Benzyl chloride
(a -Chlorotoluene)
1,1-Dichloroethane
1,1-Dichloroethylene
(Vinylidene chloride)
1,2-Dichloroethane (EDC)
1,2-Dichloroethylene
Dichloromethane
Phenol
o-Xylene
m-Xylene
p-Xylene
Pesticides and Other Compounds
(Source: PFOAM)
Quantitative Analysis
Qualitative Analysis
T-BHC (Lindane)
Hexachlorobenzene
Hexachlorocyclopentadiene (C-56)
1,2,3,4-Tetrachlorobenzene
1,2,3-Trichlorobenzene
1,2,4-Trichlorobenzene
1,3,5-Trichlorobenzene
2,4,5-Trichlorophenol
Pentachlorobenzene
Hexachloro-1,3-butadiene
1,2,4,5-Tetrachloro-
benzene
Of, a, 2 ,6-Tetrachloro-
toluene
Pentachloro-1,3-butadiene
Pentachloronitrobenzene
(PCNB)
1,2,3,5-Tetrachloro-
benzene
ce-Benzenehexachloride
(a-BHC)
Heptachlor
(continued)
169
-------
TABLE A-2 (continued)
Inorganics
(Source: HIVOL)
Quantitative Analysis
Antimony
Arsenic
Beryllium
Cadmium
Copper
Lead
Nickel
Zinc
Note: 2,3,7,8-Tetrachlorodibenzo-p-dioxin was quantitatively
determined in a select number of samples.
170
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APPENDIX B
COMPARATIVE DATA AND EXISTING STANDARDS FOR
SUBSTANCES MONITORED AT LOVE CANAL
COMPARATIVE DATA
The Love Canal multimedia environmental monitoring program
included sampling at control sites selected specifically for the
purpose of collecting comparative data that permitted the testing
of statistical hypotheses rergarding the extent and degree of
Love Canal-related contamination in the Declaration Area. Due to
limited availability of appropriate control sites and the rela-
tively short time period during which this study was to be con-
ducted, the number of control sites samples that could be col-
lected was (in certain instances) restricted. An enumeration of
control sites locations for selected medium/source/location com-
binations is presented in Table B-l.
NONCONTEMPORARY COMPARATIVE DATA
The Love Canal monitoring program was designed to include a
control area, in this case a site-specific control. Another use-
ful kind of control, however, is background data on concentra-
tions of various chemicals in pertinent media from around the
nation.
The principal problem in assembling data on national back-
ground concentrations is the lack of routine monitoring networks
for many of the chemicals of interest. Most of the data on or-
ganic chemicals, for example, were collected for regulatory pur-
poses, compliance, or enforcement, and are therefore related to
unusually high discharges or leakage of chemicals from known
sources.
There are, however, some nationwide monitoring networks that
are sources of useful data. Examples are: (1) the National Air
Sampling Network, (NASN) which collects data on metals in air
samples? (2) the National Organics Reconnaissance Survey (NORS)
for organics in drinking water; and (3) the National Urban Soil
Network (NUSN) for pesticides in soil. Other than data from such
networks, only various research projects proved fruitful.
171
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TABLE B-l. CONTROL SITES
Site Code
Address
Ground Water - A Wells (Shallow System)
95th Street, Niagara Falls (near DeMunda Avenue)
Cayuga Drive, Niagara Falls (near 98th Street)
Cayuga Drive, Niagara Falls (near 95th Street)
Jayne Park, Niagara Falls (near South 86th Street)
Niagara Falls (near Brookhaven Drive)
Niagara Falls (near Colvin Boulevard)
Niagara Falls (near Read Avenue)
Niagara Falls (near Read Avenue)
Pasadena Avenue, Niagara Falls (near Lindbergh Avenue)
Luick Avenue, Niagara Falls (near 91st Street)
Griffon Park, Niagara Falls
99015
99016
99017
99072
99550
99551
99552
99553
99554
99555
99559
99015
99016
99017
99033
99034
99072
99550
99551
99553
99555
99556
99558-B1
99558-B2
99559
99560
99008
99010
99012
99017
99020
99021
99022
99023
99051
Deuro Drive
91st Street
92nd Street
91st Street
Ground Water - B Wells (Bedrock)
95th Street, Niagara Falls (near DeMunda Avenue)
Cayuga Drive, Niagara Falls (near 98th Street)
Cayuga Drive, Niagara Falls (near 95th Street)
Jayne Park, Niagara Falls (near South 91th Street)
Buffalo Avenue, Niagara Falls (near 8Rth Street)
Jayne Park, Niagara Falls (near South 86th Street)
Deuro Drive, Niagara Falls (near Brookhaven Drive)
91st Street, Niagara Falls (near Colvin Boulevard)
91st Street, Niagara Falls (near Read Avenue)
Luick Avenue, Niagara Falls (near 91st Street)
Brookside Avenue, Niagara Falls (near 90th Street)
Williams Road, Town of Wheatfield (near Robert Moses Pkwy.)
Williams Road, Town of Wheatfield (near Robert Moses Pkwy.)
Griffon Park, Niagara Falls
Williams Road, Town of Wheatfield (near Robert Moses Pkwy.)
Soil
Frontier Avenue, Niagara Falls (near 82nd Street)
82nd Street, Niagara Falls (near Laughlin Drive)
60th Street, Niagara Falls (near Lindbergh Avenue)
Cayuga Drive, Niagara Falls (near 95th Street)
Stony Point Road, Grand Island (near Love Road)
West River Parkway, Grand Island (near White Haven Road)
Pierce Avenue, Niagara Falls (near 22nd Street)
Packard Road, Town of Niagara (near Young Street)
Woodstock Road, Grand Island (near Long Road)
(continued)
172
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TABLE B-l (continued)
Site Code Address
Sump Water
99021 West River Parkway, Grand Island (near White Haven Road)
Storm Sewer Water and Sediment
99529 91st Street, Niagara Falls (near Bergholtz Creek)
Surface Water and Stream Sediment
99004 Bergholtz Creek, Town of Wheatfield (near Williams Road)
99005 Black Creek, Town of Wheatfield (near Williams Road)
99025 Cayuga Creek, Niagara Falls (near Cayuga Drive)
99035 Fish Creek, Town of Lewiston (near Upper Mountain Road)
99073 Niagara River (approximately coincident with the imaginary
extension of 102nd Street, Niagara Falls)
A i r
99020 Stony Point Road, Grand Island (near Love Road)
99021 West River Parkway, Grand Island (near White Haven Road)
99022 Pierce Avenue, Niagara Falls (near 22nd Street)
99023 Packard Road, Town of Niagara (near Young Street)
173
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In evaluating the quality of the reported data, three desig-
nations are used: high quality (Q), which has excellent quality
control procedures? research quality (R), which has very good
quality control; and uncertain (U), which has unknown quality
control, but has results consistent with other published data.
These designations are indicated for each entry in the following
tables.
The tables that follow are of two types. One type (Table
B-2) is nationwide average data that could not be related to
specific monitoring locations. The other type (Tables B-3 through
B-5) is reported by city, where the cities have been aggregated
according to commercial cities (no significant industry), in-
dustrial cities, and chemical cities (significant chemical indus-
tries). Some of the cities included in the three categories are:
Commercial Industrial Chemical
Honolulu, HI Pittsburgh, PA Edison, NJ
Cheyenne, WY Birmingham, AL Baltimore, MD
Sacramento, CA Gary, IN Houston, TX
Phoenix, AZ St. Louis, MO Belle, WV
Ogden, UT Cincinnati, OH Pasadena, TX
Cedar Rapids, Ih Detroit, MI Passaic, NJ
Very little data were identified for the types of samples
collected in the biomonitoring program (dog and mice hair, mice
tissues, worm and crayfish tissues, and silver maple? leaves). No
analyses of such samples for organics were located. The few
analyses for metals that were located are presented in Table B-6.
The five tables of comparative data that follow include the
following information:
Chemical—the name of the chemical detected.
Range—the range of mean values reported.
Qual.—the quality of the data (Q,H,U) explained above.
Max.—the maximum value reported. A blank indicates
maximum unknown.
No.—the number of cities in that category.
Time—the years in which analyses occurred.
Table B-2 summarizes the U.S. average data that consists of
research quality, in general, and which were collected between
1964 and 1979.
BIBLIOGRAPHY
Air Quality Data for Metals 1976 from the NASN. EPA-600/4-79-Q54.
Ambient Air Carcinogenic Vapors—Improved Sampling and Analytical
Techniques and Field Studies. EPA-600/2-79-008.
174
-------
Analysis of EPA Pesticides Monitoring Networks. EPA-560/13-79-
014.
Benzo-a-Pyrene data from SAROAD.
Biological Monitoring for Environmental Pollutants. EPA-600/3-
80-089 to 092.
Cycling and Control o-f Metals, Proceedings of a Conference,
NERC-Cincinnati. February 1973.
Geochemical Environment in Relation to Health and Disease. Ann.
N.Y. Acad. Sci., vol. 199. 1972.
Monitoring to Detect Previously Unrecognized Pollutants in Sur-
face Waters. EPA-560/6-77-015.
National Organics Reconnaissance Survey for Halogenated Organics
JAWWA 67: 643-47. 1975.
Water Quality Criteria Data Book. Vol. 1 and Vol. 2. 1970-71.
175
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TABLE B-2,
U.S. AVERAGE DATA
(ppb)
Chemical
Antimony
Arsenic
Barium
Beryllium
Cadmium
Chromium
Copper
Lead
Nickel
Mercury
Selenium 0
Zinc
Lindane
Heptachlor
Aldrin
Heptachlor
epoxide
Endrin
Dieldrin
Chlordane
Toxaphene
2DDT
PCB
Triehloro-
ethene
Carbon tetra-
chloride
Tetrachloro-
ethene
1,1, 1-Trichloro-
e thane
1,2-Dichloro-
ethane
Vinyl chloride
Methylene
chloride
Soil Mean
or Range
5ppm
6ppm
0 . 3ppm
5-l,OOOppm
l-200ppm
15ppm
0.071ppm
.l-200ppm
10-300ppm
1-6
1-8
2-117
5-175
Drinking
Sediment Water
Range Range
<2-100
<10-20
<1-200
<.01-<5
<0.1-9
<0.1-11
<0. 4-980
<0. 1-100
<0.1-10
<0.5-<10
<10-3,000
0.43-1.99
3.1-21.7
1.71-5.77
2.2-48.2
0.06-3.2
0,1-30
0.1-21
0.1-3.3
0.8-4.8
0.1-9.8
0.2-13
Surface
Water
Range
10-100
1-130
1-80
0.1-20
0.005-0.76
0.005-0.031
0.001-0.26
0.001-0.067
0.005-0.94
0.003-0.17
0.006-0.075
0.5-0.75
0.012-0.292
0.006-0.12
0.1-42
0.2-10
0.1-9
0.1-1.2
0.1-45
0.2-5.1
0.4-19
176
-------
TABLE B-3. AIR
(ptg/m )
Gcwnereial Cities
Chemical
Range
Max. Qual.
o-BHC 0.0009-0.002
Lindane 0.0002-0.001
Heptachlor 0.0001-0.005
Dieldrin 0.0002-0.0004
Chlorfane 0.0008-0.018
HOT 0.002
PCS 0.004-0.068
Methylene chloride
1 , 1-Dieihloroethane
Vinyl chloride
Chloroform
1 , 2-C4cJiloroethane
1 , 2-Dichloroethene
1,1, 1-Trichloroethane
Carbon tetrachloride
Trichloroethene
1,1, 2-Trichloroethane
1 , 1 , 2 , 2-Tetrachlaro-
ethane
Benzyl chloride
Tetra-
chloroethene
Chlorobenzene
1 , 4-Dichlorobenzene
1 , 3-Diehlorobenzene
Hexachl.orobutadiene
Tridilorebenzenes
Benzo-a-Fyrene
Arsenic
Barium
Beryllium
Cacfcniun
Chronium
Copper
Lead
Nickel
Zinc
0.0003
ND-0.1
0.02-0.06
0.00019-0.00037
0.002
0.005-0.026
0.067-0.53
0.54-1.55
0.004-0.041
0.0001-0.138
0.0009
0.24
0.00055
30.18
0.043
0.83
4.19
0.079
0.44
Q
Q
Q
Q
Q
Q
Q
O
U
U
U
U
Q
Q
Q
Q
U
No.
3
3
3
3
2
1
2
1
4
5
7
1
4
7
7
7
6
Industrial Cities
Range
0.0006-0.002
0.0003-0.002
0.0003-0.009
0.0002-0.002
0.003-0.031
0.005-0.006
0.003-0.011
0,69
ND-0.44
0.3
ND-1.07
ND-0.09
ND-0.11
ND-0.066
ND-0.28
ND-0.21
ND-0.24
ND
ND
0.0001-0.002
ND-0.1
0.01-0.08
0.00018-0.00033
0.009-0.035
0.004-0.016
0.055-0.54
0.22-1.23
0.004-0.033
0.054-0.475
Max. Qual.
1.1
1.1
0.4
2.3
0.13
1.0
0.35
0.56
0.004
0.37
0.00098
0.046
0.021
0.79
1.71
0.05
0.96
Q
Q
Q
Q
Q
Q
Q
R
R
R
R
R
R
R
R
R
R
R
R
U
U
U
U
Q
Q
Q
Q
Q
U
No.
5
5
5
5
5
2
3
1
2
1
2
2
2
2
2
2
2
1
1
7
5
10
10
4
7
11
11
11
10
Chemical Cities
Range
0.7-35
0.15-22.7
2.4
T-7,8
0.022-1.1
0.25-3.4
T-1.9
0.08-2.5
0.07-2.96
0.22
0.74
0.34
0.02-1.77
ND-Q.45
0.008-0.75
0,015-0.29
0.07
ND-0.065
0.0001-0.0006
0.02-0.36
0.0001-0.0003
ND-0.001
0.005-0.034
0.068-0.31
0.83-1.84
0.004-0.047
0.06-0.272
Max. Qual.
100 R
R
R
11.1 R
9.5 R
5.3 R
7.7 R
13.7 R
10.6 R
4.5 R
1.4 R
8.0 R
9.2 R
2.6 R
R
R
0.12 R
1.16 R
0.0015 U
1.16 U
0.0013 U
0.071 0
0.072 Q
0.35 Q
3.44 Q
0.060 Q
0.77 0
No.
5
3
1
7
7
3
7
7
7
1
1
1
6
7
6
6
1
2
4
8
9
9
7
8
8
9
9
Time
1975-77
1975-77
1975-77
1975-77
1975-77
1975-77
1975-77
1976-77
1976-77
1976-77
1976-77
1976-77
1976-77
1976-77
1976-77
1976-77
1976-77
1976-77
1976-77
1976-77
1976-77
1976-77
1976-77
1976-77
1976-77
1977-78
1978-79
1978-79
1978-79
1978-79
1978-79
1978-79
1978-79
1978-79
1978-79
ND: Below limit of detection
-------
CD
TABLE B-4. SURFACE WATER (pig/liter)
(1976)
Industrial Cities
Chemical
Chloroform
1 , 2-Dichloroethane
1,1, 1-Triehloroe thane
Bromodichloromethane
Trichloroethene
Benzene
Dibromochlorome thane
1,1,2 , 2-Tetrachloroethane
Tetrachloroethene
Pentachlorophenol
1 , 4-Diehlorobenzene
Di ( 2-ethylhexyl )phthalate
Di-n-butylphthalate
Range
1-43
4-7
300
270
4-8
1
1
4
10
1-150
Qual.
R
R
R
R
R
R
R
R
R
R
No.
6
2
1
1
1
2
1
1
1
5
Chemical Cities
Range
1-87
1-9
2
1-8
1-4
1
4
1
1-5
21
2-5
1-4
Qual.
R
R
R
R
R
R
R
R
R
R
R
R
No.
4
3
1
2
3
1
3
1
2
1
4
3
-------
TABLE B-5.
DRINKING WATER (^g/liter)
(1975)
M
•xl
Commercial Cities
Compound
Chloroform
1 , 2-Diehloroethane
Carbon Tetrachloride
Bromodichlorome thane
Dibromochloromethane
Bromoform
Range
0.4-311
T
0.9-29
T-16
2-3
Qual,
Q
Q
Q
Q
Q
No.
9
3
8
7
3
Industrial Cities
Range
4-93
T-0.4
T-2
0.8-28
T-17
T-l
Qual.
Q
Q
Q
Q
Q
Q
No.
12
5
3
11
10
3
Chemical Cities
Range
0.6-86
T-6
T-3
T-16
T-5
Qual.
Q
Q
Q
Q
Q
No.
7
4
3
7
7
T: Trace
-------
TABLE B-6. BIOTA
Element
Silver Maple Leaf
Concentrations Qual.
Mouse Hair
Range Qual,
Antimony
Cadmium
Chromium
Mercury
Selenium
0
0
.1
.3
1
R
R 5,600-8
<8
200-27
,300
,200
,000
R
R
R
R
Tables B-7 and B-8 contain the results from EPA sponsored
ambient air monitoring studies. Table B-7 presents the results,
in nanograms per cubic meter (ng/m ), of measurements in ambient
air for the substances listed conducted by Research Triangle In-
stitute, as well as the results of other EPA studies (References
1, 2, and 3). Table B-8 presents the results from a study con-
ducted for EPA of air samples collected near the downtown areas
of Los Angeles and Oakland, California, and Phoenix, Arizona.
This study incorporated the use of gas chromatography with elec-
tron capture detector (ECD), or flame ionization detector (FID),
for measurement purposes.
REFERENCES FOR TABLES B-7 AND B-8
1. Pellizzari, E. D. and J. E. Bunch. Ambient Air Carcinogenic
Vapors. Improved Sampling and Analytical Techniques and
Field Studies. EPA-600/2-79-081. May 1979.
2. Pellizzari, E. D. Analysis of Organic Air Pollutants by Gas
Chromatography and Mass Spectroscopy. Final Report. EPA-
600/2-79-057. March 1979.
3. Interim Report on Monitoring Methods Development in the
Beaumont-Lake Charles Area. EPA 600/4-80-046. October 19PO
(author not listed).
4. Singh, H. B., L. J. Salas, A. Smith, and H. Shigeishi. Atmo-
spheric Measurements of Selected Toxic Organic Chemicals:
Halogenated Alkanes; Chlorinated Ethylenes, Chlorinated
Aromatics, Aromatic Hydrocarbons, and Secondary Organics.
Interim Report, Grant No. 805990, SRI Project 7774, SRI In-
ternational. April 1980.
Table B-9 summarizes the current standards for some of the
organic compounds and elements monitored in air at Love Canal.
The information reported in Table B-9 includes standards of the
U.S. Occupational Safety and Health Administration (OSHA) and
National Institute of Occupational Safety and Health (NIOSH), and
180
-------
recommended exposure limits of the American Conference of Govern-
mental Industrial Hygienists (ACGIH). The occupational standards
reported here are presented for informational purposes only, and
are not to be interpreted as applicable directly to acceptable
household or ambient exposure levels.
Table B-10 presents the analytical results from the National
Organics Reconnaissance Survey of Halogenated Organics (NORS) and
the National Organics Monitoring Survey (NOMS) of drinking water
supplies. The table contains findings for chloroform, bromoform,
bromodichloromethane, dibromochloromethane, and total trihalo-
methane concentrations in the water supplies of 80 U.S. cities
(NORS) and 113 public water systems (NOMS).
The EPA national drinking water regulations are presented in
Table B-ll. Table B-ll includes both the national interim pri-
mary drinking water regulations as well as the recommended na-
tional secondary drinking water regulations.
181
-------
TABLE B-7.
LIST OF COMPOUNDS FOUND IN AMBIENT AIR
USING TENAX
Compound
Vinyl chloride
Ethyl chloride
Vinylidene chloride
( 1 , 1-Dichloro-
ethylene)
Ethyl bromide
Methylene chloride
Location Cone. Range (ng/m )
Clifton, NJ
Passaic, NJ
Belle, WV
Nitro, WV
Deer Park, TX
Plaquemine, LA
Plaquemine, LA
Edison, NJ
Bridgeport, NJ
Linden, NJ
Staten Island, NY
Charleston, WV
Front Royal, VA
Bristol, PA
N. Philadelphia, PA
Marcus Hook, PA
Plaquemine, LA
Geismar, LA
Liberty Mounds, OK
Houston, TX
Edison, NJ
Eldorado, AK
Magnolia, AK
Paterson, NJ
Clifton, NJ
Passaic, NJ
Hoboken , NJ
Fords, NJ
Edison, NJ
E. Brunswick, NJ
Sayreville, NJ
Linden, NJ
Deepwater, NJ
Burlington, NJ
Bridgeport, NJ
Staten Island, NY
Niagara Falls, NY
Belle, WV
( continued)
400
120,000
2-4,000
50,000
100
30-1,334
1,378
T(454)
T(303)
T(263)
T(263)
T(263)
T(500)-2,500
T(333)
T(263)
T(263)
36-990
T-200
T
T-430
T-1,000
T
T
1,091
1,545
400
T
9,286
T-1,250,000
T(l,000)-125,000
T-7,600
T(500)-26,778
35-625
T(l,000)
T(555)-l,000
9778-19,500
44-11,556
8,700
Ref .
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
^T means trace; a number in parentheses by the T means estimated minimum
detectable amount under the sampling and analysis conditions.
182
-------
TABLE B-7 (continued)
Compound
Methylene chloride
(continued)
1 , 2-Dichloro-
ethylene
Chloroprene isomer
3 -Chloropropene
1 , 1-Dichloro-
e thane
Chloroform
Location Cone. Range (ng/m )
Nitro, WV
South Charleston, WV
Bristol, PA
N. Philadelphia, PA
Marcus Hook, PA
Charleston, WV
St. Albans, WV
W. Belle, WV
Institute, WV
Front Royal, VA
Birmingham, AL
Geismar, LA
Baton Rouge, LA
Houston, TX
Magna , UT
Upland, CA
E. Brunswick, NJ
Edison, NJ
Niagara Falls, NY
St. Albans, WV
W. Belle, WV
S. Charleston, WV
Nitro, WV
Institute, WV
Front Royal, VA
Magna, UT
Grand Canyon, AR
Sayreville, NJ
Edison, NJ
Edison, NJ
Linden, NJ
Deer Park, TX
Plaquemine, LA
Geismar, LA
Baton Rouge, LA
Lake Charles, LA
Magna , UT
Pater son, NJ
( continued)
T(555)-50,000
T(714)-ll,334
T(571)
T(555)-560
T(555)-l,000
T(l,000)-2,818
T(714)-778
T(714)-l,778
1,636-4,091
T(714)-238,250
T(715)-l,000
442-2,333
160-2,160
0-4,300
T(714)-23,714
1,800-42,000
4,847
T(565)-5,263
T(29)-334
T(263)
T(263)
T(213)
T(213)
T(213)
T(213)-2,974
T(334)
260
4,067
T-28,667
22,700
229
555
T-478
75,500
34-477
3,015-10,443
T(334)
3,750
Ref .
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
3
1
1
TT means trace; a number in parentheses by the T means estimated minimum
detectable amount under the sampling and analysis conditions.
183
-------
TABLE B-7 (continued)
Compound
Location
Cone. Range (ng/m )
(continued)
Ref.
Chloroform Clifton, NJ
(continued) Passaic, NJ
Hoboken, NJ
Newark, NJ
Staten Island, NY
Fords, NJ
Bound Brook, NJ
E. Brunswick, NJ
Edison, NJ
Sayreville, NJ
Linden, NJ
Deepwater, NJ
Burlington, NJ
Bridgeport, NJ
Niagara Falls, NY
S. Charleston, WV
Nitro, WV
Bristol, PA
N. Philadelphia, PA
Front Royal, VA
Marcus Hook, PA
Charleston, WV
St. Albans, WV
W. Belle, WV
Birmingham, AL
Houston, TX
Pasadena, TX
Deer Park, TX
Freeport, TX
La Porte, TX
Plaquemine, LA
Geismar, LA
Baton Rouge, LA
Magna, UT
Upland , CA
1,2-Dichloro- Paterson, NJ
ethane Clifton, NJ
Passaic, NJ
8,300
4,167
2,083
37,000
144-20,830
16,700
4,167
186-20,000
T(230)-266,000
9,000-30,000
T(75)-l,178
T-439
T(167)
250
464-13,484
T(125)-2,161
T(125)-39,000
150-250
T(97)
T(125)-14,517
T(97)-235
T(167)
T(125)
T(125)
T(125)-l,000
T(125)-ll,538
T
T-53,846
T-280
7,692-8,850
419-5,800
857-11,742
181-6,968
T(125)
400-14,000
T
64,516"
T
1
1
1
1
1
1
1
1
1
1
1,
1,
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1,
1
1,
1
1
1
1
1
2
2
2
2
'T means trace; a number in parentheses by the T means estimated minimum
detectable amount under the sampling and analysis conditions.
184
-------
TABLE B-7 (continued)
Compound Location Cone. Range (ng/m }
1 , 2-Dichloro- Hoboken, NJ
ethane Newark, NJ
(continued) Fords, NJ
Bound Brook, NJ
Edison, NJ
Sayreville, NJ
E. Brunswick, NJ
Linden, NJ
Deepwater, NJ
Burlington, NJ
Bridgeport, NJ
Staten Island, NY
St. Albans, WV
W. Belle, WV
Charleston, WV
Nitro, WV
S. Charleston, WV
Institute, WV
Front Royal , VA
Bristol, PA
N. Philadelphia, PA
Marcus Hook, PA
Birmingham, AL
Houston, TX
Pasadena, TX
Deer Park, TX
Freeport, TX
La Porte, TX
Plaquemine, LA
Geismar, LA
Baton Rouge, LA
Lake Charles, LA
Magna, UT
Dominquez, CA
Upland, CA
1, 1 , 1-Trichloro- Paterson, NJ
ethane Clifton, NJ
Passaic, NJ
{ continued)
T
T
T
T
T(347)-57,000
37,913
T(150)
T(151)-101
T-53
T
T(195)
T(195)
T(334)
T(213)
T(212)
T(151)
T(263)
T(213)
T(213)-2,974
T(258)
T(195)-960
T(195)
200-400
T(258)-242
158
T-66,300
3,300-4,500
778
10-3,700
100-10,333
78-10,341
21-1,240
T(334)
14,814
T( 277) 860
T
T
13,000
Ref .
1
1
1
1
1
I
1
1,2
1,2
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
'T means trace; a number in parentheses by the T means estimated minimum
detectable amount under the sampling and analysis conditions.
185
-------
TABLE B-7 (continued)
Compound Location Cone
1,1,1-Trichloro- Hoboken, NJ
ethane Newark, NJ
(continued) staten Island, NY
Fords, NJ
Bound Brook , NJ
Edison, NJ
E. Brunswick, NJ
Sayreville, NJ
Linden, NJ
Deepwater, NJ
Burlington, NJ
Bridgeport, NJ
Niagara Falls, NJ
S. Charleston, WV
Bristol, PA
N. Philadelphia, PA
Marcus Hook, PA
Charleston, WV
St. Albans, WV
Nitro, WV
W. Belle, WV
Institute, WV
Front Royal, VA
Birmingham, AL
Houston, TX
Pasadena, TX
Deer Park, TX
Freeport, TX
La Porte, TX
Plaquemine, LA
Geismar, LA
Baton Rouge, LA
Liberty Mounds, OK
Tulsa, OK
Vera , OK
Beaumont, TX
Lake Charles, LA
Magna, UT
( continued)
. Range (ng/m )
T
T
T
T
T
T(417)-500,000
T(417)
T-30
T-3,116
T-2,842
T(294)
129-650
T(334)-3,890
T(312)-5,000
T(267)
T(277)
T-1,600
T(217)-278
T(334)
T(334)
T(312)
T(217)-347
T(100)-2,933
T(334)-2,267
522-995
T
144-1,000
15,200-16,600
T-27,700
68-8700
T-675
78-500
T-(417)
T(334)
T(334)
727-8,381
32-35,000
T(334)
Ref .
1
I
1
1
1
1
1
1
1
1
1
1
1
I
I
I
I
I
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
3
1,3
1
T means trace; a number in parentheses by the T means estimated minimum
detectable amount under the sampling and analysis conditions.
186
-------
TABLE B-7 (continued)
Compound Location Cone. Range (ng/m )
1 , 1 , 1-Trichloro- Grand Canyon, AR
ethane Lqs Angeles, CA
(continued) Upland, CA
Carbon tetrachloride Paterson, NJ
Clifton, NJ
Passaic, NJ
Hoboken , NJ
Newark, NJ
Staten Island, NY
Fords, NJ
Bound Brook, NJ
East Brunswick, NJ
Edison, NJ
Sayreville, NJ
Linden, NJ
Deepwater, NJ
Burlington, NJ
Bridgeport, NJ
Niagara Falls, NY
S. Charleston, WV
Bristol, PA
N. Philadelphia, PA
Marcus Hook, PA
Nitro, WV
W. Belle, WV
St. Albans, WV
Institute, WV
Front Royal, VA
Houston, TX
Pasadena, TX
Deer Park, TX
Freeport, TX
La Porte, TX
Plaquemine, LA
Geismar, LA
Baton Rouge, LA
Liberty Mounds, OK
Tulsa, OK
( continued )
T(217)-218
8340
T(454)-51,721
T
T(59)
T
T
T
T(74)
334
T
T(120)-20,000
T-13,687
T(125)
T-71
19-32
T(125)
T(74)
T(83)-5,038
T(95)-2,222
T(95)
T(74)
T(74)
T(95)
T(91)
T(74)-3,630
T(59)-441
T(59)-l,190
T(87)-238
T-146
T-846
T-11,538
T-1,230
T-4,628
183-10,100
74-1,037
T
T
Ref .
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
^T means trace; a number in parentheses by the T means estimated minimum
detectable amount under the sampling and analysis conditions.
187
-------
TABLE B-7 (continued)
Compound
Carbon tetrachloride
(continued)
Dibromomethane
l-Chloro-2-bromo-
ethane
1,1, 2-Trichloro-
ethane
Trichloroethylene
Location Cone. Range (ng/m )
Vera, OK
Beaumont, TX
Lake Charles, LA
Magna, UT
Grand Canyon, AR
Upland , CA
Paterson, NJ
Edison, NJ
E. Brunswick, NJ
Edison, NJ
El Dorado, AK
Magnolia, AK
Edison, NJ
Sayreville, NJ
Ed i son , NJ
Linden, NJ
Deer Park, TX
Freeport, TX
Plaquemine, LA
Geismar, LA
Baton Rouge, LA
Lake Charles, LA
Paterson, NJ
Clifton, NJ
Passaic, NJ
Hoboken, NJ
Staten Island, NY
Bound Brook , NJ
Edison, NJ
E. Brunswick, NJ
Sayreville, NJ
Linden, NJ
Deepwater, NJ
Burlington, NJ
Bridgeport, NJ
Niagara Falls, NY
Charleston, WV
S. Charleston, WV
( continued)
T
611-16,380
30-10,154
T(95)-166
T(59)
T(134)-l,461
130
63,000
42
5,000-27,000
T-73
32-1,089
294-17,571
3,500
4,467
200
3,334-6,700
T-3,821
36-1,840
120-9,611
54-553
3,500-40,400
1,200
T
T
T
T(73)
T
T(178)-93,000
T-82,000
T-3,737
T-242
4-56
T(92)
T(77)
T(73)-15,880
T(56)
T(55)-179
Ref .
1
3
1,3
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
3
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
^T means trace; a number in parentheses by the T means estimated minimum
detectable amount under the sampling and analysis conditions.
18B
-------
TABLE B-7 (continued)
Compound Location Cone. Range (ng/m )
Trichloroethylene Nitro, WV
(continued) St. Albans, WV
Bristol, PA
N. Philadelphia, PA
Marcus Hook, PA
W. Belle, WV
Institute, WV
Front Royal, VA
Birmingham, AL
Houston, TX
Pasadena, TX
Deer Park, TX
Freeport, TX
La Porte, TX
Baton Rouge, LA
Lake Charles, LA
Beaumont, TX
Liberty Mounds, OK
Tulsa, OK
Magna , UT
Grand Canyon, AR
Dominquez, CA
Upland, CA
1 , 2-Dibromoethane Sayreville, NJ
Edison, NJ
Deepwater, NJ
Beaumont, TX
El Dorado, AK
Magnolia, AK
Tetrachloroethylene Paterson, NJ
Clifton, NJ
Passaic, NJ
Hoboken, NJ
Newark, NJ
Staten Island, NY
Fords, NJ
Bound Brook, NJ
Edison, NJ
( continued )
T(55)-360
T(98)-45
T(100)
T(92)
T(80)
T(55)
T(55)
T(74)-420
T(100)-134
T(100)-160
76-5,071
321
0-200
T-43
T(132)
392-6,000
0-1,034
T
T
T(100)
T(130)
9,210
T(167)-3,400
591
T-757
T
0-1,000
T-271,283
26-62,484
T
T
T
T
T
T
T
T
T-394,000
Ref .
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
3
3
1
1
1
1
1
1
1
1
1
3
1
1
1
1
1
1
1
1
1
1
1
^T means trace; a number in parentheses by the T means estimated minimum
detectable amount under the sampling and analysis conditions.
189
-------
TABLE B-7 (continued)
Compound Location Cone
Tetrachloroethylene E. Brunswick, NJ
(continued) Sayreville, NJ
Deepwater, NJ
Burlington, NJ
Bridgeport, NJ
Linden, NJ
Niagara Falls, NY
Charleston, WV
S. Charleston, WV
St. Albans, WV
Nitro, WV
W. Belle, WV
Institute, WV
Front Royal, VA
Birmingham, AL
Houston, TX
Pasadena, TX
Deer Park, TX
Freeport, TX
La Porte, TX
Lake Charles, LA
Beaumont, TX
Plaquemine , LA
Geismar, LA
Baton Rouge , LA
Liberty Mounds, OK
Tulsa, OK
Vera, OK
Magna, UT
Grand Canyon, AR
Dominquez, CA
Upland, CA
Chlorobenzene Pater son, NJ
Clifton, NJ
Hoboken, NJ
Newark, NJ
Staten Island, NY
Fords, NJ
Bound Brook, NJ
{ continued )
. Range (ng/m )
T-2,722
T(49)-60,000
T-218
185
T(189)-276
T(106)-960
T(155)-51,992
T(19)-109
T(35)-l,536
T(26)-434
T(19)-52
T(19)
T(19)
T(19)-2,994
T{25)-58
T(44)-260
T-20
T-2,019
0-1,585
T-83
T-10,547
0-3,900
T-1,224
7-100
T(59)-364
T
T
T
T(34)-80
T{234)
20,000
70-7,258
T
T
T
T
T(135)
T
20,000
Ref .
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
3
3
1
1
1
I
I
1
1
1
1
1
1
1
1
1
1
1
1
*T means trace; a number in parentheses by the T means estimated minimum
detectable amount under the sampling and analysis conditions.
190
-------
TABLE B-7 (continued)
Compound
Chlorobenzene
( continued )
1,1,2, 2-Tetrachloro-
ethane
Chlorotoluene
isomer ( s )
Pentachloroethane
m-Di chlorobenzene
Location Cone
E. Brunswick, NJ
Edison, NJ
Sayreville, NJ
Linden, NJ
Deepwater, TX
Burlington, NJ
Bridgeport, NJ
Niagara Falls, NY
S. Charleston, WV
Nitro, WV
Charleston, WV
W. Belle, WV
Bristol, PA
N. Philadelphia, PA
Marcus Hook, PA
Institute, WV
Front Royal, VA
Birmingham, AL
Plaquemine, LA
Geismar, LA
Baton Rouge, LA
Houston, TX
Lake Charles, LA
Beaumont , TX
Magna, UT
Grand Canyon, AR
Upland, CA
Edison, NJ
Baton Rouge, LA
Iberville Parish, LA
Lake Charles, LA
Niagara Falls, NY
Iberville Parish, LA
Linden, NJ
Iberville Parish, LA
Clifton, NJ
Hoboken, NJ
Newark , NJ
(continued )
3 t
. Range (ng/m )
T(77)-l,127
T(60)-12,791
T{60)-4,000
T-272
11-512
T(278)
T(231)
T(197)-4,232
T(18)
T(18)
T(18)
T(18)
450
T(238)
T(242)
T(18)
T(18)
38-122
29
T-900
T(128)
T(132)-125
7-29
T-1100
T(100)
T(104)
T(136)-152
1,389-2,2785
0-71
0-5,800
37-430
25-226,514
0-35
76
0-13
T(33)
T{33)
T{33)
Ref .
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1,3
3
1
1
1
1
2
2
3
1
2
1
2
1
1
1
'T means trace; a number in parentheses by the T means estimated minimum
detectable amount under the sampling and analysis conditions.
191
-------
TABLE B-7 (continued)
Compound Location Cone
m-Dichlorobenzene Bound Brook, NJ
(continued) Edison, NJ
East Brunswick, NJ
Sayreville, NJ
Linden, NJ
Deepwater, NJ
Burlington, NJ
Bridgeport, NJ
Staten Island, NY
S. Charleston, WV
St. Albans, WV
Nitro, WV
Institute, WV
W. Belle, WV
Front Royal, VA
Bristol, PA
N. Philadelphia, PA
Marcus Hook, PA
Charleston, WV
Birmingham, AL
Baton Rouge, LA
Houston, TX
El Dorado, AK
Lake Charles, LA
Magna , UT
Grand Canyon, AR
Upland, CA
o-Dichlorobenzene Edison, NJ
East Brunswick, NJ
Sayreville, NJ
Linden, NJ
Deepwater, NJ
Burlington, NJ
Bridgeport, NJ
Staten Island, NY
South Charleston, WV
Nitro, WV
St. Albans, WV
( continued)
. Range (ng/m )
T(33)
T(49)-33,783
T(33)-659
T(72)-126
T-78
T-1,240
T(185)
T(154)
T(90)
T-38
T(18)
T(20)
T(12)
T(9)
T(17)-279
T(172)
T{167)
T(161)
101
T(94)-557
T(85)
T(83)
16
6-27
T{69)
T(260)
T(26)-382
T(49)~12,433
T(33)-l,500
T
T--89
T-1,319
T(185)
T
T(90)
T(17)-309
T(9)-39
T(23)
Ref .
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1,3
1
1
1
1
1
1
1
1
1
1
1
1
1
1
^T means trace? a number in parentheses by the T means estimated minimum
detectable amount under the sampling and analysis conditions.
192
-------
TABLE B-7 continued)
Compound
Location
Cone. Range (ng/m )
isomers
Bromotoluene isomer
Dichlorotoluene
isomer(s)
Benzyl Chloride
Chloroaniline isomer
Trichlorobenzene
isomer
Edison, NJ
Niagara Falls, NY
Ford, NJ
Deepwater, NJ
Niagara Falls, NY
Edison, NJ
Bound Brook, NJ
Deepwater, NJ
Bound Brook, NJ
Edison, NJ
Linden, NJ
Deepwater, NJ
Niagara Falls, NY
Front Royal, VA
Bristol, PA
N. Philadelphia, PA
Upland, CA
Deer Park, TX
(continued)
472-1,873
T(53)-4372
T
29-107
T(106)-158,682
4,513-8,033
33
T-5,960
867
1,160
T-113
T-150
T(23)-43,700
T(7)
T(103)
T
T(43)
25-2,000
Ref .
o-Dichlorobenzene
( continued)
Dichlorobenzene
isomers
Chlorobenzaldehyde
W. Belle, WV
Institute, WV
Front Royal, VA
Bristol, VA
N. Philadelphia, PA
Baton Rouge, LA
Tulsa, OK
Houston, TX
Lake Charles, LA
Upland, CA
Fords, NJ
Bound Brook, NJ
Linden, NJ
Deepwater, NJ
Niagara Falls, NY
Liberty Mounds, OK
Tulsa, OK
Niagara Falls, NY
T(8)
T(9)-59
T(13)-58
T(172)
T(167)-185
T(84)
T
T(86)
T
T(26)
T
T
T-30
T-1,240
T(29)-100,476
80
T
T(18)-4,058
1
1
1
1
1
1
1
1
1,3
1
1
1
2
2
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
1
^T means trace; a number in parentheses by the T means estimated minimum
detectable amount under the sampling and analysis conditions.
193
-------
TABLE B-7 (continued)
Compound
Location
Cone. Range (ng/m )
butadiene
Bromopropane isomer
Allyl bromide
1, 2-Dichloropropane
Bromodichloro-
methane
Chlorodibromo-
methane
Dichloropropane
isomers
El Dorado, AK T-47
Magnolia, AK T-734
El Dorado, AK T-30
Magnolia, AK 9-16
Geismar, LA 36-3,999
Beaumont, TX 0-1,450
Lake Charles, LA 23
Iberville Parish, LA 0-2,200
El Dorado, AK T-26
Magnolia, AK T
El Dorado, AK T-81
Lake Charles, LA 34-230
Deer Park, TX T-2,586
Preeport, TX 69-1,478
Plaquemine, LA T-2,239
(continued)
Ref.
Trichlorobenzene
isomer
( continued )
1 , 3-Hexachloro-
butadiene
Chloronitrobenzene
isomer
Dichloronitro-
benzene isomer
Tetrachloro-
benzene isomer(s)
Tetrachloro-
toluene isomer(s)
Pentachlorobenzene
2~Chloro-l,3-
Freeport, TX
La Porte, TX
Plaquemine, LA
Baton Rouge, LA
Niagara Falls, NY
Deer Park, TX
Freeport, TX
La Porte, TX
Plaquetnine, LA
Baton Rouge, LA
Lake Charles, LA
Deepwater, NJ
Deepwater, NJ
Niagara Falls, NY
Niagara Falls, NY
Niagara Falls, NY
Houston, TX
8-13
T
20-40
23-117
26-414
25-2,066
T
T
18-37
23-117
T-12
T-360
T-2,704
T(21)-9,600
16-970
T(23)-494
266-4,000
1
1
1
1
1
1
1
1
1
1
3
1
1
1
1
1
1
1
1
1
1
1
3
1
2
1
1
1
1,3
1
1
1
'T means trace; a number in parentheses by the T means estimated minimum
detectable amount under the sampling and analysis conditions.
194
-------
TABLE B-7 (continued)
Compound
Location
Cone. Range (ng/m )
Ref.
Dibromochloro-
propane isomer(s)
Dichlorobutane
isomer(s}
l-Chloro-2,3-
dibromopropane
1,l-Dibromo-2-
Chloropropane
1,2 & 1,3-Dibromo-
propane
Dichlorodibromo-
methane
Chlorobromo-
propane isomer
l-Chloro-3-bromo-
propane
l-Chloro-3-bromo-
propene
Bichloropropene
isomer
Bromoform
Bromobenzene
Tetrachlorobutadiene
Tetrachloropropane
isomer
Benzene
Acetone
Cyanobenzene
(benzonitrile}
Furan
El Dorado, AK
Magnolia, AK
p'laquemine, LA
Baton Rouge, LA
El Dorado, AK
El Dorado, AK
El Dorado, AK
Magnolia, AK
El Dorado, AK
El Dorado, AK
El Dorado, AK
Magnolia, AK
El Dorado, AK
Deer Park, TX
Plaquemine, LA
El Dorado, AK
Magnolia, AK
Lake Charles, LA
El Dorado, AK
Magnolia, AK
Iberville Parish, LA
Iberville Parish, LA
Iberville Parish, LA
Baton Rouge, LA
Beaumont, TX
Linden, NJ
Baton Rouge, LA
Linden, NJ
Deepwater, NJ
Lake Charles, LA
Linden, NJ
Deepwater, NJ
(continued)
T-187
25-6,653
54-7,200
13-193
T-20
T
T
7-40
T-83
T-23
T-1,688
T
T-1,293
10-260
T-104
8-380
68-729
T-4,276
23-140
0-17
0-240
420-16,000
80-11,000
900-33,333
43-21,300
68-3,294
T-49
T-35
19-62
9-46
T-59
1
1
1,2
1,2
1
1
1
1
1
1
1
1
1,3
1
1
2
2
2
2
3
2
2
2
2
3
2
2
'T means trace; a number in parentheses by the T means estimated minimum
detectable amount under the sampling and analysis conditions.
195
-------
TABLE B-7 (continued)
Compound
Location
Cone. Range (ng/m )
Ref.
t-Butanol
iso-Propanol
Methylethyl ketone
Benzaldehyde
Acetophenone
Methylvinyl ketone
Cyclohexanone
Diethyl maleate
Diethyl fumarate
Tolualdehyde
Methylmethacrylate
Dibenzofuran
Phenylacetylene
Nitrobenzene
Aniline (or
methylpyridine)
Chloroaniline isomer
Nitrophenol
o-Nitrotoluene
p-Nitrotoluene
1 , 2-Dibromopropane
Toluene
Ethyl benzene
Naphthalene
Xylene( s }
1-Methylnaphthalene
n-Nonanal
Ethyl acetate
Linden, NJ
Linden, NJ
Linden, NJ
Linden, NJ
Linden, NJ
Lake Charles, LA
Linden, NJ
Deepwater, NJ
Linden, NJ
Linden, NJ
Linden, NJ
Linden, NJ
Deepwater, NJ
Deepwater, NJ
Deepwater, NJ
Deepwater, NJ
Deepwater, NJ
Deepwater, NJ
Deepwater, NJ
Deepwater, NJ
Deepwater, NJ
Lake Charles, LA
Lake Charles, LA
Beaumont, TX
Lake Charles, LA
Beaumont, TX
Lake Charles, LA
Beaumont, TX
Lake Charles, LA
Lake Charles, LA
Beaumont, TX
87-1,745
4-59
T-84
36-557
131-1,167
133-270
10-45
T-72
T-629
T-1,085
T-882
T-83
16-95
29-3,279
T-41
105-123
28
T-5,960
24-73
T-47
59-86
23
290-2,179
1378-32,157
57-354
102-3,598
56-118
32-26,765
T-24
260-1,105
T-933
2
2
2
2
2
3
2
2
2
2
2
2
2
2
2
2
2
2
2
2
2
3
3
3
3
3
3
3
3
3
3
"T means trace; a number in parentheses by the T means estimated minimum
detectable amount under the sampling and analysis conditions.
196
-------
TABLE B-8.
AVERAGE DAILY CONCENTRATIONS OF TOXIC CHEMICALS
POUND BY SINGH*
Compounds
Methyl chloride
Methyl bromide
Methylene chloride
Chloroform
Carbon tetrachloride
1 , 2-Dichloroe thane
1 , 2-Dibromoethane
1,1, 1-Trichloroethane
1,1, 2-Trichloroethane
1,1,1, 2-Tetrachloroethane
1,1,2, 2-Tetrachloroethane
Vinylidene chloride
Trichloroethylene
Tetrachloroethylene
Chlorobenzene
o-Dichlorobenzene
m-Dichlorobenzene
1,2, 4-Trichlorobenzene
Benzene
Toluene
Ethylbenzene
m/p-Xylenes
o-Xylene
4-Ethyl toluene
1,2, 4-Trimethylbenzene
1,3, 5-Trimethylbenzene
Phosgene
Peroxyacetyl nitrate
Peroxypropionyl nitrate
Los Angeles
3,002
244
3,751
88
215
519
33
1,028
9
4
17
5
399
1,480
200
125
77
69
6,040
11,720
2,250
4,610
1,930
1,510
1,880
380
-
4,977
722
Phoenix
2,391
67
893
111
277
216
40
824
16
9
17
30
484
994
200
226
87
31
4,740
8,630
2,000
4,200
1,780
1,510
1,740
400
_
779
93
Oakland
1,066
55
416
32
169
83
16
291
8
4
7
13
188
308
100
40
65
30
1,550
3,110
600
1,510
770
660
-
_
50
356
149
'See Reference 4.
197
-------
TABLE B-9. SUMMARY OF CURRENT STANDARDS FOR SUBSTANCES
MONITORED IN LOVE CANAL AIR SAMPLES
Substance
Benzene
Carbon
tetrachloride
Chloroben zene
o-Chlorotoluene
p-Chlorotol uene
1, 2-Dibromo-
ethane
o-Dichloro-
benzene
p-Dichloro-
benzene
1, 1, 2,2-Tetra-
chloroethylene
Toluene
OSHAf
Environmental
Standards
lOppm, 8 hr. TWA
(30 mg/m3)
lOppm, 8 hr. TWA
(65 mg/m3)
75ppm, 8 hr. TWA
__
—
20ppm, 8 hr. TWA
(152 mg/m3)
SQppm, ceiling
(300 mg/m3}
75ppm, 8 hr. TWA
(450 mg/m3)
lOOppm, 8 hr. TWA
(678 mg/in3)
200ppm, -B hr. TWA
(750 mg/m3)
NIOSH*
Recommended
Limit
Ippm ceiling
(3.2 mg/m3)
(60-minute)
2ppm ceiling
(12.6 mg/m )
( 60-minute)
—
__
—
0.13ppm ceiling
( 1 mg/m3 )
{ 15-minute)
— ,**
-_—
SOppm, 1,0 hr.
TWA ..
(339 mg/nT)
lOOppm, 10 hr.
TWA -
(375 mg/m )
(continued)
ACGIH*
Adopted
Value
30 mg/m ,
TLV-TWA
65 mg/m »
TLV-TWA
350 mg/m ,
TLV-TWA
250 mg/m ,
TLV-TWA
—
no
exposure
3
300 mg/m
ceiling
450 mg/m
TLV-TWA
670 mg/m
TLV-TWA
375 mg/m
TLV-TWA
NIOSH
Considered
Health Effect
blood changes,
including
leukemia
liver cancer
—
_ —
—
damage to
skin , eyes ,
heart, liver,
spleen, res-
piratory and
central ner-
vous systems;
potential for
cancer and
mut agenesis
__
-.—
nervous system.
heart, respira-
tory, liver
central nervous
system depres-
sant
198
-------
TABLE B-9 (continued)
Substance
OSHA'
Environmental
Standards
NIOSH*
Recommended
Limit
ACGIH* NIOSH
Adopted Considered
Value Health Effect
y-BHC
(Lindane)
Hexachloro-
benzene
Hexachlorocyclo-
pentadiene
(C-56)
1,2,3,4-Tetra-
ehlorobenzene
1,2,3-Trichloro-
benzene
1,2,4-Trichloro-
benzene
1,3,5-Trichloro-
benzene
2,4,5-Trichloro-
phenol
Pentachloro-
benzene
0.5 rag/in"
TLV-TWA
0.1 mg/m"
TLV-TWA
40 mg/m
TLV-TWA
Antimony
Arsenic
Beryllium
Cadmium
0,5 mg/m , 8 hr.
TWA
0.01 mg/m ,
8 "hr. TWA
0.002 mg/m3,
8 hr. TWA
0.1 mg/m , 8 hr.
TWA
0 . 5 mg/m ,
10 hr. TWA
0.002 mg/m
ceiling
(15-minute )
0.0005 mg/m3
(130-minute)
0.04 mg/m ,
10 hr. TWA
0.5 mg/in
TLV-TWA
0 . 2 mg/m3
TLV-TWA
0.002 mg/m3
TLV-TWA
0.05 mg/m ,
TLV-TWA
irritation;
heart and lung
effects
dermatitis,
lung and lym-
phatic cancer
lung cancer
lung and kidney
effects
(continued)
199
-------
TABLE B-9 (continued)
Substance
Copper
Lead
OSHA^
Environmental
Standards
0.05 mg/m ,
8 hr. TWA
NIOSH*
Recommended
Limit
0.
10
1 mg/m ,
hr , TWA
ACGIH*
Adopted
Value
1 mg/m
TLV-TWA
0,15 mg/m3
TLV-TWA
NIOSH
Considered
Health Effect
kidney, blood,
and nervous
Nickel
Zinc
1 mg/m , 8 hr.
TWA
0.015 mg/m"
10 hr. TWA
1 mg/m
TLV-TWA
system effects
skin effects;
nasal cancer
TU.S. Occupational Safety and Health Administration (OSHA) environmental stand-
ards as of March 1, 1981. The phrase "8 hr. TWA" means the time-weighted av-
erage concentration, for a normal 8-hour workday or 40-hour workweek, to which
nearly all workers may be exposed without adverse effect; the phrase "ceiling"
means the concentration maximum to which workers may be exposed,
*The National Institute of Occupational Safety and Health (NIOSH) recommended
work-place exposure limits as of March 1, 1981. Values are reported as "ceil-
ing" or time-weight average; the health effects considered in the establish-
ment of the limit are also listed in the table,
*The American Conference of Governmental Industrial Hygienists (ACGIH) thresh-
old limit values (TLV) for chemical substances in workroom air adopted for
1980. Threshold limit values "refer to airborne concentrations of substances
and represent conditions under which it is believed that nearly all workers
may be repeatedly exposed day after day without adverse effect. Because of
wide variation in individual susceptibility, however, a small percentage of
workers may experience discomfort from some substances at concentrations at or
below the threshold limit; a smaller percentage may be affected more seriously
by aggravation of a pre-existing condition or by development of an occupa-
tional illness." Values are reported as "ceiling" or time-weighted average.
Note: Values repotted are in parts per million (ppm) and milligrams per cubic
meter (mg/m') . To convert from milligrams to micrograms, use 1 mg =
1,000 jig.
200
-------
TABLE B-10.
ANALYTICAL RESULTS OF CHLOROFORM, BROMOFORM, BROMODICHLOROMETHANE,
AND DIBROMOCHLOROMETHANE, AND TOTAL TRIHALOMETHANES IN
WATER SUPPLIES FROM NORS AND NOMS1"
{Concentrations in milligrams per liter, ppm)
Compound
NORS
NOMS
Phase I Phase II
Phase III
Dechlorinated Terminal
to
O
Chloroforms
Bromoform;
D ib rompchlo r o-
methane:
B romodichlorp—
methane:
Total Trihalo-
Median 0.021
Mean —
Range NF-0.311
Median 0.005
Mean —
Range NF-0.092
Median 0.001
Mean
Range NF-0.100
Median 0.006
Mean —
Range NF-Q.116
0.027
0.043
NF-0.271
LD
0.003
NF-0.039
LD
0.008
NF-0.19
0.010
0.018
NF-0.183
0.059
0.083
NF-0.47
LD
0.004
NF-0.280
0.004
0.012
NF-0.290
0.014
0.018
NF-0.180
0.022
0.035
NF-0.20
LD
0.002
NF-0.137
0.002
0.006
NF-0.114
0.006
0.009
NF-0.072
0.044
0.069
NF-0,540
LD
0.004
NF-0.190
0.003
0.011
NF-0.250
0.011
0.017
NF-0.125
methanes:
NF:
LD:
Not Found
Less than
Median
Mean
Range
Detection
0.027
0.067
NF-0.482
Limit
0
0
NF-0
.045
.068
.457
0
0
NF-0
.087
.117
.784
0
0
NF-0
.037
.053
.295
0
0
NF-0
.074
.100
.695
'The National Organics Reconnaissance Survey of Halogenated Organics {NORS)
involved 80 U.S. cities. The National Organics Monitoring Survey {NOMS)
involved 113 public water systems. Phase I of NOMS is comparable to NORS.
Phase II analyses were performed after THM-producing reactions were al-
lowed to run to completion. Phase III analyses were conducted on both
dechlorinated samples and on samples that were allowed to run to comple-
tion {terminal).
-------
TABLE B-ll. EPA NATIONAL DRINKING WATER REGULATIONS
National Interim Primary
Drinking Water Regulations^
(milligrams per liter, ppm)
Recommended National Secondary
Drinking Water Regulations*
(milligrams per liter, ppm)
Inorganics
Maximum
Contaminant Level
Inorganics
Maximum
Contaminant Level
Arsenic
Barium
Cadmium
Chromium
Lead
Mercury
Nitrate (as N)
Selenium
Silver
Fluoride
0.05
1. 0
0. 01
0.05
0.05
0.002
10.0
0.01
0.05
1.4 - 2.4"
Chloride
Copper
Iron
Manganese
Sulfate
Zinc
Total Dissolved
Sol ids
250.0
1.0
0. 3
0.05
250.0
5.0
500.0
Organics
Edrin 0.0002
Y-BHC (Lindane) 0.004
Methoxychlor 0.1
Toxaphene 0.005
2,4-Dichlorophenoxy-
acetic acid (2,4-D) 0.1
2,4,5-Trichlorophenoxy-
propionic acid
(2,4,5-TP Silvex) 0.01
Total Trihalomethanes 0.1
As published in the Federal Register, Vol. 40, No. 248, December 24,
1975, 59566, and subsequently amended
^Selected contaminants reported from: National Secondary Drinking
Water Regulations, EPA-570/9-76-000, July, 1979
*The fluoride standard varies according to the annual average maximum
daily air temperature for the location in which the community water
system is situated.
Note: Total trihalomethanes is the sum of chloroform, dibromochloro-
methane, bromodichloromethane, and bromoform rounded to two
significant figures.
202
-------
The following information has been extracted from an article
published by EPA in the Federal Register, Vol. 45, No. 231.
November 28, 1980. The material has been provided here to sum-
marize current EPA water quality criteria.
SUMMARY OF WATER QUALITY CRITERIA
Acenaphthene
Freshwater Aquatic Life
The available data for acenaphthene
indicate that acute toxicity to freshwater
aquatic life occurs at concentrations as
low as 1,700 ng/1 and would occur at
tower concentrations among species
that are more sensitive than those
tested. No data are available concerning
the chronic toxicity of acenaphthene to
sensitive freshwater aquatic animals but
toxicity to freshwater algae occur at
concentrations as low as 520 fig/1.
Saltwater Aquatic Life
The available data for acenaphthene
indicate that acute and chronic toxicity
to saltwater aquatic life occur at
concentrations as low as 970 and 710
fig/1, respectively, and would1 occur at
lower concentrations among species
that are more sensitive than those
tested. Toxicity to algae occurs at
concentrations as low as 500 fig/1.
Human Health
Sufficient data is not available for
acenaphthene to derive a level which
would protect against the potential
toxicity of this compound. Using
available organoleptic data, for
controlling undesirable taste and odor
quality of ambient water, the estimated
level is 20 jtg/L It should be recognized
that organoleptic data as a basis for
establishing a water quality criteria
have limitations and have no
demonstrated relationship to potential
adverse human health effects.
Acrolein
Freshwater Aquatic Life
The available data for acrolein
indicate that acute and chronic toxicity
to freshwater aquatic life occurs at
concentrations as low as 68 and 21 u.g/1,
respectively, and would occur at lower
concentrations among species that are
more sensitive than those tested.
Saltwater Aquatic Life
The available data for acrolein
indicate that acute toxicity to saltwater
aquatic life occurs at concentrations as
low as 55 jig/1 and would occur at lower
concentrations among species that are
more sensitive than those tested. No
data are available concerning the
chronic toxicity of acrolein to sensitive
saltwater aquatic life.
Human Health
For the protection of human health
from the toxic properties of acrolein
ingested through water and
contaminated aquatic organisms, the
ambient water criterion is determined to
be 320 u.g/1.
For the protection of human health
from the toxic properties of acrolein
ingested through contaminated aquatic
organisms alone, the ambient water
criterion is determined to be 780 (ig/1,
Acrylonitrile
Freshwater Aquatic Life
The available data for acrylonitrile
indicate that acute toxicity to freshwater
aquatic life occurs at concentrations as
low as 7,550 ftg/1 and would occur at
lower concentrations among species
that are more sensitive than those
tested. No definitive data are available
concerning the chronic toxicity of
acrylonitrile to sensitive freshwater
aquatic life but mortality occurs at
concentrations as low as 2,600 ftg/1 with
a fish species exposed for 30 days.
Saltwater Aquatic Life
Only one saltwater species has been
tested with acrylonitrile and no
statement can be made concerning acute
or chronic toxicity.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of acrylonitrile
through ingestion of contaminated water
and contaminated aquatic organisms,
the ambient water concentration should
be zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk over the lifetime are
estimated at W~*, 10"*, and 10"'. The
corresponding criteria are ,58 fig/1, .058
fig/1 and .006 fig/1, respectively. If the
above estimates are made for
consumption of aquatic organisms only,
excluding consumption of water, the
levels are 6.5 fig/1, .65 fig/1, and .065 fig/
1, respectively. Other concentrations
representing different risk levels may be
calculated by use of the Guidelines. The
risk estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level.
Aldrin-Dieldrin
Dieldrin
Fresh water Aquatic Life
For dieldrin the criterion to protect
fresh water aquatic life as derived using
the Guidelines is 0.0019 ftg/1 as a 24-
hour average and the concentration
should not exceed 2.5 fig/1 at any time.
Saltwater Aquatic Life
For dieldrin the criterion to protect
saltwater aquatic life as derived using
the Guidelines is 0.0019 fig/1 as a 24-
hour average and the concentration
should not exceed 0.71 fig/1 at any time.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of dieldrin
through ingestion of contaminated water
and contaminated aquatic organisms,
the ambient water concentration should
be zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk over the lifetime are
estimated at ID"5,10"s, and 10"'. The
corresponding criteria are .71 ng/1, .071
ng/1, and .0071 ng/1, respectively. If the
above estimates are made for
consumption of aquatic organisms only,
excluding consumption of water, the
levels are .76 ng/1, .076 ng/1, and .0076
ng/1 respectively. Other concentrations
representing different risk levels may be
calculated by use of the Guidelines. The
risk estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level,
Aldrin
Freshwater Aquatic Life .
For freshwater aquatic life the
concentration of aldrin should not
exceed 3.0 fig/1 at any time. No data are
available concerning the chronic toxicity
of aldrin to sensitive freshwater aquatic
life.
Saltwater Aquatic Life
For saltwater aquatic life the
concentration of aldrin should not
exceed 1.3 fig/1 at any time. No data are
available concerning the chronic toxicity
of aldrin to sensitive saltwater aquatic
life.
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Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of aldrin through
ingestion of contaminated water and
contaminated aquatic organisms, the
ambient water concentration should be
zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk over the lifetime are
estimated at 10"5, 10"6, and 10"7. The
corresponding criteria are .74 ng/1, .074
ng/1, and .0074 ng/1, respectively. If the
above estimates are made for
consumption of aquatic organisms only,
excluding consumption of water, the
levels are .79 ng/1, .079 ng/1, and .0079
ng/1, respectively. Other concentrations
respresenting different risk levels may
be calculated by use of the Guidelines.
The risk estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level.
Antimony
Freshwater Aquatic Life
The available data for antimony
indicate that acute and chronic toxicity
to freshwater aquatic life occur at
concentrations as low as 9,000 and 1,600
Hg/1, respectively, and would occur at
lower concentrations among species
that are more sensitive than those
tested. Toxicity to algae occurs at
concentrations as low as 610 fig/1.
Saltwater Aquatic Life
No saltwater organisms have been
adequately tested with antimony, and
no statement can be made concerning
acute or chronic toxicity.
Human Health
For the protection of human health
from the toxic properties of antimony
ingested through water and
contaminated aquatic organisms, the
ambient water criterion is determined to
be 146 fig/1.
For the protection of human health
from the toxic properties of antimony
ingested through contaminated aquatic
organisms alone, the ambient water
criterion is determined to be 45,000 jig/1.
Arsenic
Freshwater Aquatic Life
For freshwater aquatic life the
concentration of total recoverable
trivalent inorganic arsenic should not
exceed 440 fig/1 at any time. Short-term
effects on embryos and larvae of aquatic
vertebrate species have been shown to
occur at concentrations as low as 40 fig/
1.
Saltwater Aquatic Life
The available data for total
recoverable trivalent inorganic arsenic
indicate that acute toxicity to saltwater
aquatic life occurs at concentrations as
low as 508 fig/1 and would occur at
lower concentrations among species
that are more sensitive than those
tested. No data are available concerning
the chronic toxicity of trivalent
inorganic arsenic to sensitive saltwater
aquatic life.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of arsenic
through ingestion of contaminated water
and contaminated aquatic organisms,
the ambient water concentration should
be zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk over the lifetime are
estimated at 10"5,10"6. and 10"'. The
corresponding criteria are 22 ng/1, 2.2
ng/1, and .22 ng/1, respectively. If the
above estimates are made for
consumption of aquatic organisms only.
excluding consumption of water, the
levels are 175 ng/1, 17.5 ng/1, and 1.75
ng/1, respectively. Other concentrations
representing different risk levels may be
calculated by use of the Guidelines. The
risk estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level.
Asbestos
Freshwater Aquatic Life
No freshwater organisms have been
tested with any asbestiform mineral and
no statement can be made concerning
acute or chronic toxicity.
Saltwater Aquatic Life
No saltwater organisms have been
tested with any asbestiform mineral and
no statement can be made concerning
acute or chronic toxicity.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of asbestos
through ingestion of contaminated water
and contaminated aquatic organisms,
the ambient water concentration should
be zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk over the lifetime are
estimated at 10"5, 10"6, and 10"'. The
corresponding criteria are 300,000
fibers/1,30,000 fibers/1, and 3,000 fibers/
1, respectively. Other concentrations
representing different risk levels may be
calculated by use of the Guidelines. The
risk estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level.
Benzene
Freshwater Aquatic Life
The available data for benzene
indicate that acute toxicity to freshwater
aquatic life occurs at concentiations as
low as 5,300 fig/I and would occur at
lower concentrations among species
that are more sensitive than those
tested. No data are available concerning
the chronic toxicity of benzene to
sensitive freshwater aquatic life.
Saltwater Aquatic Life
The available data for benzene
indicate that acute toxicity to saltwater
aquatic life occurs at concentrations as
low as 5,100 fig/1 and would occur at
lower concentrations among species
that are more sensitive than those
tested. No definitive data are available
concerning the chronic toxicity of
benzene to sensitive saltwater aquatic
life, but adverse effects occur at
concentrations as low as 700 fig/1 with a
fish species exposed for 168 days.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of benzene
through ingestion of contaminated water
and contaminated aquatic organisms,
the ambient water concentration should
be zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk over the lifetime are
estimated at 'LO"5. 10"6, and 10"1. The
corresponding ^criteria are 6.6 fig/1, .66
fig/1, and .066 fig/1, respectively. If the
above estimates are made for
consumption of aquatic organisms only,
excluding consumption of water, the
levels are 400 fig/1, 40.0 fig/1, and 4.0 fig/
1, respectively. Other concentrations
representing different risk levels may be
calculated by use of the Guidelines. The
204
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risk estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level.
Benzidine
Freshwater Aquatic Life
The available data for benzidine
indicate that acute toxicity to freshwater
aquatic life occurs at concentrations as
low as 2,500 ng/1 and would occur at
lower concentrations among species
that are more sensitive than those
tested. No data are available concerning
the chronic toxicity of benzidine to
sensitive freshwater aquatic life.
Saltwater Aquatic Life
No saltwater organisms have been
tested with benzidine and no statement
can be made concerning acute and
chronic toxicity.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of benzidine
through ingestion of contaminated water
and contaminated aquatic organisms,
the ambient water concentration should
be zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk over the lifetime are
estimated at 10'', 10"«, and 10"7. The
corresponding criteria are 1.2 ng/1, .12
ng/1, and .01 ng/1, respectively. If the
above estimates are made for
consumption of aquatic organisms only,
excluding consumption of water, the
levels are 5.3 ng/1, .53 ng/1, and .05 ng/
1, respectively. Other concentrations
representing different risk levels may be
calculated by use of the Guidelines. The
risk estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level.
Beryllium
Freshwater Aquatic Life
The available data for beryllium
indicate that acute and chronic toxicity
to freshwater aquatic life occurs at
concentrations as low as 130 and 5.3 ng/
1, respectively, and would occur at lower
concentrations among species that are
more sensitive than those tested.
Hardness has a substantial effect on
acute toxicity.
Salt water Aquatic Life
The limited saltwater data base
available for beryllium does not permit
any statement concerning acute or
chronic toxicity.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of beryllium
through ingestion of contaminated water
and contaminated aquatic organisms,
the ambient water concentration should
be zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk over the lifetime are
estimated at 10"5,10" 6, and 10"'. The
corresponding criteria are 37 ng/1, 3.7
ng/1, and .37 ng/1, respectively. If the
above estimates are made for
consumption of aqua tic. organisms only,
excluding consumption of water, the
levels are 641 ng/1. 64.1 ng/1, and 6.41
ng/1, respectively. Other concentrations
representing different risk levels may be
calculated by use of the Guidelines. The
risk estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level.
Cadmium
Freshwater Aquatic Life
For total recoverable cadmium the
criterion (in ng/1) to protect freshwater
aquatic life as derived using the
Guidelines is the numerical value given
by e(i-«tto|-»M» ag a 24-hour
average and the concentration (in ng/1)
should not exceed the numerical value
given by e(1" n-o«*—>l-n» at any
time. For example, a hardnesses of 50,
100, and 200 mg/1 as CaCO, the criteria
are 0.012,0.025, and 0.051 ug/1,
respectively, and the concentration of
total recoverable cadmium should not
exceed 1.5, 3.0 and 6.3 ftg/1, respectively,
at any time.
Saltwater Aquatic Life
For total recoverable cadmium the .
criterion to protect saltwater aquatic life
as derived using the Guidelines is 4.5
ng/1 as a 24-hour average and the
concentration should not exceed 59 ng/1
at any time.
Human Health
The ambient water quality criterion
for cadmium is recommended to be
identical to the existing drinking water
standard which is 10 (ig/1. Analysis of
the toxic effects data resulted in a
calculated level which is protective of
human health against the ingestion of
contaminated water and contaminated
aquatic organisms. The calculated value
is comparable to the present standard.
For this reason a selective criterion
based on exposure solely from
consumption of 6.5 grams of aquatic
organisms was not derived.
Carbon Tetrachloride
Freshwater Aquatic Life
The available date for carbon
tetrachloride indicate that acute toxicity
to freshwater aquatic life occurs at
concentrations as low as 35,200 ng/1 and
would occur at lower concentrations
among species that are more sensitive
than those tested. No data are available
concerning the chronic toxicity of
carbon tetrachloride to sensitive
freshwater aquatic life.
Saltwater Aquatic Life
The available data for carbon
tetrachloride indicate that acute toxicity
to saltwater aquatic life occurs at
concentrations as low as 50,000 fig/1 and
would occur at lower concentrations
among species that are more sensitive
that those tested. No data are available
concerning the chronic toxicity of
carbon tetrachloride to sensitive
saltwater aquatic life.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of carbon
tetrachloride through ingestion of
contaminated water and contaminated
aquatic organisms the ambient water
concentration should be zero based on
the non-threshold assumption for this
chemical. However, zero level may not
be attainable at the present time.
Therefore, the levels which may result in
incremental increase of cancer risk over
the lifetime are estimated at 10"', 10"',
and 10"'. The corresponding criteria are
4.0ng/l, .40 fig/1, and .04 ng/1.
respectively. If the above estimates are
made for consumption of aquatic
organisms only, excluding consumption
of water, the levels are 69.4 ng/1. 6-94
ng/1, and .69 n8/l> respectively. Other
concentrations representing different
risk levels may be calculated by use of
the Guidelines. The risk estimate range
is presented for information purposes
and does not represent an Agency
judgment on an "acceptable" risk level.
Chlordane
Freshwater Aquatic Life
For chlordane the criterion to protect
freshwater aquatic life as derived using
the Guidelines is 0.0043 ng/1 as a 24-
hour average and the concentration
should not exceed 2.4 ng/1 at any time.
Saltwater Aquatic Life
For chlordane the criterion to protect
saltwater aquatic life as derived using
the Guidelines is 0.0040 ng/' as a 24-
hour average and the concentration
should not exceed 0.09 ng/1 at any time.
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Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of chlordane
through ingestion of contaminated water
and contaminated aquatic organisms,
the ambient water concentration should
be zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk over the lifetime are
estimated at 10"', 10"*, and 10"'. The
corresponding criteria are 4,8 ng/1, ,46
ng/1, and .046 ng/1, respectively. If the
above estimates are made for
consumption of aquatic organisms only,
excluding consumption of water, the
levels are 4.8 ng/1, .48 ng/1, and .048 ng/
1, respectively. Other concentrations
representing different risk levels may be
calculated by use of the Guidelines. The
risk estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level.
Chlorinated Benzenes
Fresh water Aquatic Life
The available data for chlorinated
benzenes indicate that acute toxicity to
freshwater aquatic life occurs at
concentrations aa low a* 250 ftg/1 and
would occur at lower concentrations
among species thai are more sensitive
than those tested No data are available
concerning the chronic toxicity of the
more toxic of the chlorinated benzenes
to sensitive freshwater aquatic life but
toxicity occurs at concentrations as low
as 50 jig/1 for a fish species exposed for
7,5 days.
Saltwater Aquatic Lifa
The available data for chlorinated
benzenes indicate that acute and
chronic toxicity to saltwater aquatic life
occur at concentrations as low as 180
and 129 ug/1, respectively, and would
occur at lower concentrations among
species that are more sensitive than
those tested.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of
hexachlorobenzene through ingestion of
contaminated water and contaminated
aquatic organisms, the ambient water
concentration should be zero based on
the non-threshold assumption for this
chemical. However, zero level may not
be attainable at the present time.
Therefore, the levels which may result in
incremental increase of cancer risk over
the lifetime are estimated at 10~6,10"*.
and 10"'. The corresponding
recommended criteria are 7.2 ng/1, .72
ng/1, and .072 ng/1, respectively. If the
above estimates are made for
consumption of aquatic organisms only,
excluding consumption of water, the
levels are 7.4 ng/1, .74 ng/1, and .074 ng/
1, respectively.
For the protection of human health
from the toxic properties of 1,2,4,5-
tetrachlorobenzene ingested through
water and contaminated aquatic
organisms, the ambient water criterion
is determined to be 38 fig/1.
For the protection of human health
from the toxic properties of 1,2,4,5-
tetrachlorobenzene ingested through
contaminated aquatic organisms alone,
the ambient water criterion is
determined to be 48 fig/1.
For the protection of human health
from the toxic properties, of
pentachlorobenzene ingested through
water and contaminated aquatic
organisms, the ambient water criterion
is determined to be 74 fig/1.
For the protection of human health
from the toxic properties of
pentachlorobenzene ingested through
contaminated aquatic organisms alone,
the ambient water criterion is
determined to be 85 ng/1.
Using the present guidelines, a
satisfactory criterion cannot be derived
at this time due to the insufficiency in
the available data for trichlorobeniene.
For comparison purposes, two
approaches were used to derive
criterion levels for monochlorobenzen*.
Based on available toxicity date, for the
protection of public health, the derived
level is 488 j*g/l Using available
organoleptic data, for controlling
undesirable taste and odor quality of
ambient water, the estimated level is 20
jig/1. It should be recognized that
organoleptic data as a basis for
establishing a water quality criteria
have (imitations and have no
demonstrated relationship to potential
adverse human health effects
Chlorinated Ethanes
Freshwater Aguatic Life
The available freshwater data for
chlorinated ethanes indicate that
toxicity increases greatly with
increasing chlormation, and thai acute
toxicity occurs at concentrations as low
as 118,000 fig/1 for 1,2-dichloroethane,
18,000 ftg/1 for two trichloroethanes,
9,320 fig/1 for*two tetrachloroethanes,
7,240 fig/1 for pentachioroethane, and
980 jtg/1 for hexachloroethane. Chronic
toxicity occurs at concentrations as low
as 20,000 p.g/1 for 1,2-dichloroethane,
9,400 fig/l for 1,1,2-trichlorocthane, 2,400
fig/1 for 1,1,2,2,-tetrachloroethane, 1,100
fig/1 for pentachioroethane, and 540 fig/1
for hexachloroethane. Acute and
chronic toxicity would occur at lower
concentrations among species that are
more sensitive than those tested.
Saltwater Aquatic Life
The available saltwater data for
chlorinated ethanes indicate that
toxicity increases greatly with
increasing chlor nation and that acute
toxicity to fish and invertebrate species
occurs at concentrations as low as
113,000 fig/1 for 1,2-dichloroethane,
31,200 ftg/1 for 1,1,1-trichloroethane,
9,020 fig/1 for 1,1,2,2-tetrachloroethane,
390 jig/1 for peril achloroethane, and 940
fig/1 for hexachloroethane. Chronic
toxicity occurs at concentrations as low
as 281 ng/1 for pentachioroethane. Acute
and chronic toxicity would occur at
lower concentrations among species
that are more sensitive than those
tested.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of 1,2-di-
chloroethane through ingestion of
contaminated water and contaminated
aquatic organisms, the ambient water
concentration should be zero based on
the non-threshold assumption for this
chemical. However, zero level may not
be attainable at the present time.
Therefore, the levels which may result in
incremental increase of cancer risk over
the lifetime are estimated at 10""*, 10"*,
and 10"', The corresponding criteria are
9.4 fig/1, ,94 fig/i, and .094 p.g/1,
respectively. If the above estimates are
made for consumption of aquatic
organisms only, excluding consumption
of water, the levels are 2,430 fig/1, 243
ftg/1, and 24,3 pg/i respectively. Other
concentrations representing different
risk levels may be calculated by use of
the Guidelines. The risk estimate range
is presented for information purposes
and does not represent an Agency
judgment on an "acceptable" risk level.
For the protection of human health
from the toxic properties of 1,1,1-
trichloroe thane ingested through water
and contaminated aquatic organism, the
ambient water criterion is determined to
be 18.4 mg/1.
For the pr&tecfion of human health
from the toxic properties of 1,1,1,-tri-
chloroethane ingested through
contaminated aquatic organisms alone,
the ambient water criterion is
determined to be 1,03 g/1.
For the maximum protection of human
health from the potential carcinogenic
206
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effects due to exposure of 1,1,2-
trichloroethane through ingestion of
contaminated water and contaminated
aquatic organisms, the ambient water
concentration should be zero based on
the non-threshold assumption for this
chemical. However, zero level may not
be attainable at the present time.
Therefore, the levels which may result in
incremental increase of cancer risk over
the lifetime are estimated at 10"s, 10" s,
and 10"'. The corresponding criteria are
6,0 jig/1, .6 fig/1, and .06 ftg/1,
respectively. If the above estimates are
made for consumption of aquatic
organisms only, excluding consumption
of water, the levels are 418 fig/1, 41.8
Hg/1, and 4.18 fig/1 respectively. Other
concentrations representing different
risk levels may be calculated by use of
the Guidelines. The risk estimate range
is presented for information purposes
and does not represent an Agency
judgment on an "acceptable" risk level.
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of 1,1,2,2-tetra-
chloroethane through ingestion of
contaminated water and contaminated
aquatic organisms, the ambient water
concentration should be zero based on
the non-threshold assumption for this
chemical. However, zero level may not
be attainable at the present time.
Therefore, the levels which may result in
incremental increase of cancer risk over
the lifetime are estimated at 10"*, 10"*,
and 10" *. The corresponding criteria are
1,7 jig/1, .17 fig/1 and .017 fig/1,
respectively. If the above estimates are
made far consumption of aquatic
organisms only, excluding consumption
of water, the levels are 107 jig/1,10,7
fig/L and 1.07 |tg/l, respectively. Other
concentrations representing different
risk levels may be calculated by use of
the Guidelines. The risk estimate range
is presented for information purposes
and does not represent an Agency
judgment on an "acceptable" risk level.
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of hexa-
chloroethane through ingestion of
contaminated water and contaminated
aquatic organisms, the ambient water
concentration should be zero based on
the non-threshold assumption for this
chemical. However, zero level may not
be attainable at the present time.
Therefore, the levels which may result in
incremental increase of cancer risk over
the lifetime are estimated at 10"5.10"f,
and 10"'. The corresponding criteria are
19 fig/1,1.9 fig/1, and .19 fig/1,
respectively. If the above estimates are
made for consumption of aquatic
organisms only, excluding consumption
of water, the levels are 87.4 fig/1, 8.74
fig/1, and ,87 ftg/1, respectively. Other
concentrations representing different
risk levels may be calculated by use of
the Guidelines, The risk estimate range
is presented for information purposes
and does not represent an Agency
judgment on an "acceptable" risk level.
Using the present guidelines, a
satisfactory criterion cannot be derived
at this time due to the insufficiency in
the available data for
monochloroethane.
Using the present guidelines, a
satisfactory criterion cannot be derived
at this time dsie to the insufficiency in
the available data for 1,1,-
dichloroe thane.
Using the present guidelines, a
satisfactory criterion cannot be derived
at this time due to the insufficiency in
the available data for 1,1,1,2-
tetrachloroethane.
Using the present guidelines, a
satisfactory criterion cannot be derived
at this time due to the insufficiency in
the available data for
pentachloroe thane.
Chlorinated Naphthalenes
Freshwater Aquatic Life
The available data for chlorinated
naphthalenes indicate that acute
toxicity to freshwater aquatic life occurs
at concentrations as low as 1,600 fig/t
and would occur at lower
concentrations among species that are
more sensitive than those tested, No
data are available concerning the
chronic toxicity of chlorinated
naphthalenes to sensitive Freshwater
aquatic life.
Saltwater Aquatic Life
The available data for chlorinated
napthalsnes indicate that acute toxicity
to saltwater aquatic life occurs at
concentrations as low as 7.5 ftg/i and
would occur at lower concentrations
among species that are more sensitive
than those tested. No data are available
concerning the chronic toxicity of
chlorinated naphthalenes to sensitive
saltwater aquatic life.
Human Health
Using the present guidelines, a
satisfactory criterion cannot be derived
at this time due to the insufficiency in
the available data for chlorinated
napthalenes.
Chlorinated Phenols
Freshwater Aquatic Life
The available freshwater data for
chlorinated phenols indicate that
toxicity generally increases with
increasing chJorination, and that acute
toxicity occurs at concentrations as low
as 30 fig/1 for 4-chloro-3-methyIphenol to
greater than 500,000 fig/1 for other
compounds. Chronic toxicity occurs at
concentrations as low as 970 fig/1 for
2,4,6-trichlorophenol. Acute and chronic
toxicity would occur at lower
concentrations among species that are
more sensitive than those tested.
Saltwater Aquatic Life
The available saltwater data for
chlorinated phenols indicate that
toxicity generally increases with
increasing chlorination and that acute
toxicity occurs at concentrations as low
as 440 fig/1 for 2,3,5,8-tetrachlorophenol
and 29,700 fig/1 for 4-chlorophenol.
Acute toxicity would occur at lower
concentrations among species that are
more sensitive than those tested. No
data are available concerning the
chronic toxicity of chlorinated phenols
to sensitive saltwater aquatic life.
Human Health
Sufficient data is not available for 3-
monochlorophenol to derive a level
which would protect against the
potential toxicity of this compound.
Using available organoleptic data, for
controlling undesirable taste and odor
quahty of ambient water, the estimated
level is 0.1 ftg/1. It should be recognized
that organoleptic data as a basis for
establishing a water quality criteria
have limitations arid have no
demonstrated relationship to potential
adverse human health effects.
Sufficient data is not available for 4-
monochlorophenol to derive a level
which would protect against the
potential toxicity of this compound.
Using available organolsptic data, for
controlling undesirable taste and odor
quality of ambient water, the estimated
level is 0.1 fig/1. It should be recognized
that organoieptic data as a basis for
establishing a water quality criteria
have limitations and have no
demonstrated relationship to potential
adverse human health effects.
Sufficient data is not available for 2,3-
dichlorophenol to derive a level which
would protect against the potential
toxicity of this compound. Using
available organoleptic data, for
controlling undesirable taste and odor
quality of ambient water, the estimated
level is .04 fig/1. It should be recognized
that organoleptic data as a basis for
establishing a water quality criteria
have limitations and have no
demonstrated relationship to potential
adverse human health effects.
Sufficient data is not available for 2,5-
tlichiorophenol to derive a level which
207
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would protect against the potential
toxicity of this compound. Using
available organoleptic data, for
controlling undesirable taste and odor
quality of ambient water, the estimated
level is .5 fig/1. It should be recognized
that organoleptic data as a basis for
establishing a water quality criteria
have limitations and have no
demonstrated relationship to potential
adverse human health effects.
Sufficient data is not available for 2,6-
dichlorophenol to derive a level which
would protect against the potential
toxicity of this compound. Using
available organoleptic data, for
controlling undesirable taste and odor
quality of ambient water, the estimated
level is .2 fig/1. It should be recognized
that organoleptic data as a basis for
establishing a water quality criteria
have limitations and have no
demonstrated relationship to potential
adverse human health effects.
Sufficient data is not available for 3,4-
dichlorophenol to derive a level which
would protect against the potential
toxicity of this compound. Using
available organoleptic data, for
controlling undesirable taste and odor
quality of ambient water, the estimated
level is .3 fig/1. It should be recognized
that organoleptic data as a basis for
establishing a water quality criteria
have limitations and have no
demonstrated relationship to potential
adverse human health effects.
Sufficient data is not available for
2,3,4,6-tetrachlorophenol to derive a
level which would protect against the
potential toxicity of this compound.
Using available organoleptic data, for
controlling undesirable taste and odor
quality of ambient water, the estimated
level is 1 fig/1. It should be recognized
that organoleptic data as a basis for
establishing a water quality criteria
have limitations and have no
demonstrated relationship to potential
adverse human health effects.
For comparison purposes, two
approaches were used to derive
criterion levels for 2,4,5-trichlorophenol.
Based on available toxicity data, for the
protection of public health, the derived
level is 2.6 mg/1. Using available
organoleptic data, for controlling
undesirable taste and odor quality of
ambient water, the estimated level is 1.0
fig/1. It should be recognized that
organoleptic data as a basis for
establishing a water quality criteria
have limitations and have no
demonstrated relationship to potential
adverse human health effects.
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of 2,4,6-
trichlorophenol through ingestion of
contaminated water and contaminated
aquatic organisms, the ambient water
concentration should be zero based on
the non-threshold assumption for this
chemical. However, zero level may not
be attainable at the present time.
Therefore, the levels which may result in
incremental increase of cancer risk over
the lifetime fare estimated at 10"s, 10~6,
and 10"'. The corresponding criteria are
12 fig/1,1.2 fig/1, and .12 fig/1
respectively. If the above estimates are
made for consumption of aquatic
organisms only, excluding consumption
of water, the levels are 36 fig/1, 3.6 fig/1,
and .36 fig/1, respectively. Other
concentrations representing different
risk levels may be calculated by use of
the Guidelines. The risk estimate range
is presented for information purposes
and does not represent an Agency
judgment on an "acceptable" risk level.
Using available organoleptic data, for
controlling undesirable taste and odor
quality of ambient water, the estimated
level is 2 fig/1. It should be recognized
that organoleptic data as a basis for
establishing a water quality criterion
have limitations and have no
demonstrated relationship to potential
adverse human health effects.
Sufficient data is not available for 2-
methyl-4-chlorophenql to derive a level
which would protect against any
potential toxicity of this compound.
Using available organoleptic data, for
controlling undesirable taste and odor
quality of ambient water, the estimated
level is 1800 ng/1. It should be
recognized that organoleptic data as a
basis for establishing a water quality
criterion have limitations and have no
demonstrated relationship to potential
adverse human health effects.
Sufficient data is not available for 3-
methyl-4-chlorophenol to derive a level
which would protect against the
potential toxicity of this compound.
Using available organoleptic data, for
controlling undesirable taste and odor
quality of ambient water, the estimated
level is 3000 fig/1. It should be
recognized that organoleptic data as a
basis for establishing a water quality
criterion have limitations and have no
demonstrated relationship to potential
adverse human health effects.
Sufficient data is not available for 3-
methyl-6-chlorophenol to derive a level
which would protect against the
potential toxicity of this compound.
Using available organoleptic data, for
controlling undesirable taste and odor
quality of ambient water, the estimated
level is 20 fig/1. It should be recognized
that organoleptic data as a basis for
establishing a water quality criterion
have limitations and have no
demonstrated relationship to potential
adverse human health effects.
ChloroalkyI Ethers
Freshwater Aquatic Life
The available data for chloroalkyl
-ethers indicate that acute toxicity to
freshwater aquatic life occurs at
concentrations as low as 238,000 fig/1
and would occur at lower
concentrations among species that are
more sensitive than those tested. No
definitive data are available concerning
the chronic toxicity of chloroalkyl ethers
to sensitive freshwater aquatic life.
Saltwater Aquatic Life
No saltwater organisms have been
tested with any chloroalkyl ether and no
statement can be made concerning acute
and chronic toxicity.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of bis-
(chloromethyl)-ether through ingestion
of contaminated water and
contaminated aquatic organisms, the
ambient water concentration should be
zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk over the lifetime are
estimated at 10"*, 10"*, and 10"7. The
corresponding criteria are .038 ng/1,
.0038 ng/1, and .00038 ng/1, respectively.
If the above estimates are made for
consumption of aquatic organisms only,
excluding consumption of water, the
levels are 18.4 ng/1,1.84 ng/1, and .184
ng/1, respectively. Other concentrations
representing different risk levels may be
calculated by use of the Guidelines. The
risk estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level.
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of bis (2-
chloroethyl) ether through ingestion of
contaminated water and contaminated
aquatic organisms, the ambient water
concentration should be zero based on
the non-threshold assumption for this
chemical. However, zero level may not
be attainable at the present time.
Therefore, the levels which may result in
incremental increase of cancer risk over
the lifetime are estimated at 10"6,10"*,
and 10"7. The corresponding criteria are
.3 jig/l, .03 ug/1, and .003 fig/I,
20R
-------
respectively. If the above estimates are
made for consumption of aquatic
organisms only, excluding consumption
of water, the levels are 13.6 fig/1,1.36
fig/1, and .136 fig/1, respectively. Other
concentrations representing different
risk levels may be calculated by use of
the Guidelines. The risk estimate range
is presented for information purposes
and does not represent an Agency
judgment on an "acceptable" risk level.
For the protection of human health
from the toxic properties of bis (2-
chloroisopropyl) ether ingested through
water and contaminated aquatic
organisms, the ambient water criterion
is determined to be 34.7 jig/L
For the protection of human health
from the toxic properties of bis (2-
chloroisopropyl) ether ingested through
contaminated aquatic organisms alone.
the ambient water criterion is
determined to be 4.36 mg/1.
Chloroform
Freshwater Aquatic Life
The available data for choloroform
indicate that acute toxicity to freshwater
aquatic life occurs at concentrations as
low as 26,900 fig/1, and wculd occur at
lower concentrations among species
that are more sensitive than the three
tested species. Twenty-seven-day LC50
values indicate that chronic toxicity
occurs at concentrations as low as 1,240
Hg/1, and could occur at lower '
concentrations among species or other
life stages that are more sensitive than
the earliest life cycle stage of the
rainbow trout.
Saltwater Aquatic Life
The data base for saltwater species is
limited to one test and no statement can
be made concerning acute or chronic
toxicity.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of chloroform
through ingestion of contaminated water
and contaminated aquatic organisms,
the ambient water concentration should
be zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk over the lifetime are
estimated at 10-', lO'", and 10~7. The
corresponding criteria are 1.90 /ig/1. .19
fig/1, and .019 ftg/1, respectively. If the
above estimates are made for
consumption of aquatic organisms only,
excluding consumption of water, the
levels are 157 ftg/1.15.7 jig/1, and 1.57
fig/1, respectively. Other concentrations
representing different risk levels may be
calculated by use of the Guidelines. The
risk estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level.
2-Chlorophenol
Freshwater Aquatic Life
The availabe data for 2-chlorophenol
indicate that acute toxicity to freshwater
aquatic life occurs at concentrations as
low as 4,380 fig/1 and would occur at
lower concentrations among species
that are more sensitive that those tested.
No definitive data are available
concerning the chronic toxicity of 2-
chlorophenol to sensitive freshwater
aquatic life but flavor impairment occurs
in one species of fish at concentrations
as low as 2,000 fig/1.
Saltwater Aquatic Life
No saltwater organisms have been
tested with 2-chlorophenol and no
statement can be made concerning acute
and chronic toxicity.
Human Health
Sufficient data is not available for 2-
chlorophenol to derive a level which
would protect against the potential
toxicity of this compound. Using
available organoleptic data, for
controlling undesirable taste and odor
quality of ambient water, the estimated
level is 0.1 fig/1. It should be recognized
that organoleptic data as a basis for
establishing a water quality criteria
have limitations and have no
demonstrated relationship to potential
adverse human health effects.
Chromium
Freshwater Aquatic Life
For total recoverable hexavalent
chromium the criterion to protect
freshwater aquatic life as derived using
the Guidelines is 0.29 fig/1 as a 24-hour
average and the concentration should
not exceed 21 fig/1 at any time.
For freshwater aquatic life the
concentration (in fig/1) of total
recoverable trivalent chromium should
not exceed the numerical value given by
"e(1.08[ln(hardness)] + 3.48)" at any
time. For example, at hardnesses of 50,
100 and 200 mg/1 as CaCO, the
concentration of total recoverable
trivalent chromium should not exceed
2,200, 4,700, and 9,900 fig/1, respectively,
at any time. The available data indicate
that chronic toxicity to freshwater
aquatic life occurs at concentrations as
low a 44 fig/1 and would occur at lower
concentrations among species that are
more sensitive than those tested.
Saltwater Aquatic Life
For total recoverable hexavalent
chromium the criterion to protect
saltwater aquatic life as derived using
the Guidelines is 18 ftg/1 as a 24-hour
average and the concentration should
not exceed 1,260 fig/1 at any time.
For total recoverable trivalent
chromium, the availabe data indicate
that acute toxicity to saltwater aquatic
life occurs at concentrations as low as
10,300 fig/1, and would occur at lower
concentrations amoung species that are
more sensitive than those tested. No
data are available concerning the
chronic toxicity of trivalent chromium to
sensitive saltwater aquatic life.
Human Health
For the protection of human health
from the toxic properties of Chromium
III ingested through water and
contaminated aquatic organisms, the
ambient water criterion is determined to
be 170 mg/1.
For the protection of human health
from the toxic properties of Chromium
III ingested through contaminated
aquatic organisms alone, the ambient
water criterion is determined to be 3433
mg/1.
The ambient water quality criterion
for total Chromium VI is recommended
to be identical to the existing drinking
water standard which is 50 fig/1.
Analysis of the toxic effects data
resulted in a calculated level which is
protective of human health against the
ingestion of contaminated water and
contaminated aquatic organisms. The
calculated value is comparable to the
present standard. For this reason a
selective criterion based on exposure
solely from consumption of 6.5 grams of
aquatic organisms was not derived.
Copper
Freshwater Aquatic Life
For total recoverable copper the
criterion to protect freshwater aquatic
life as derived using the Guidelines is 5.6
ftg/1 as a 24-hour average and the
concentration (in ftg/1) should not
exceed the numerical value given by
e(0.94[ln(hardness)]-1.23) at any time.
For example, at hardnesses of 50,100,
and 200 mg/1 CaCO, the concentration
of total recoverable copper should not
exceed 12, 22, and 43 u.g/1 at any time.
Saltwater Aquatic Life
For total recoverable copper the
209
-------
criterion to protect saltwater aquatic life
as derived using the Guidelines is 4.0
fig/1 as a 24-hour average and the
concentration should not exceed 23 fig/1
at any time.
Human Health
Sufficient data is not available for
copper to derive a level which would
protect against the potential toxicity of
this compound. Using available
organoleptic data, for controlling
undesirable taste and odor quality of
ambient water, the estimated level is 1
mg/1. It should be recognized that
organoleptic data as a basis for
establishing a water quality criteria
have limitations and have no
demonstrated relationship to potential
adverse human health effects.
Cyanide
Freshwater Aquatic Life
For free cyanide (sum of cyanide
present as HCN and CN~, expressed as
CN) the criterion to protect freshwater
aquatic life as derived using the
Guidelines is 3.5 jig/1 as a 24-hour
average and the concentration should
not exceed 52 jig/1 at any time.
Saltwater Aquatic Life
The available data for free cyanide
(sum of cyanide present as HCN and
CN", expressed as CN) indicate that
acute toxicity to saltwater aquatic life
occurs at concentrations as low as 30
fig/1 and would occur at lower
concentrations among species that are
more sensitive than those tested. If the
acute-chronic ratio for saltwater
organisms is similar to that for
freshwater organisms, chronic toxicity
would occur at concentrations as low as
2.0 ng/1 for the tested species and at
lower concentrations among species
that are more sensitive than those
tested.
Human Health
The ambient water quality criterion
for cyanide is recommended to be
identical to the existing drinking water
standard which is 200 fig/I. Analysis of
the toxic effects data resulted in a
calculated level which is protective of
human health against the ingestion of
contaminated water and contaminated
aquatic organisms. The calculated value
is comparable to the present standard.
For this reason a selective criterion
based on exposure solely from
consumption of 6.5 grams of aquatic
organisms was not derived.
DDT and Metabolites
Freshwater Aquatic Life
DDT
For DDT and its metabolites the
criterion to protect freshwater aquatic
life as derived using the Guidelines is
0.0010 fig/1 as a 24-hour average and the
concentration should not exceed 1.1 fig/1
at any time.
TDK
The available data for TDE indicate
that acute toxicity to freshwater aquatic
life occurs at concentrations as low as
0.6 jig/1 and would occur at lower
concentrations among species that are
more sensitive than those tested. No
data are available concerning the
chronic toxi.jity.of TDE to sensitive
freshwater aquatic life.
DDE
The available data for DDE indicate
thdt acute toxicity to freshwater aquatic
life occurs at concentrations as low as
1,050 fig/1 and would occur at lower
concentrations among species that are
more sensitive than those tested. No
data are available concerning the
chronic toxicity of DDE to sensitive
freshwater aquatic life.
Saltwater Aquatic Life
DDT
For DDT and its metabolites the
criterion to protect saltwater aquatic life
as derived using the Guidelines is 0.0010
fig/1 as a 24-hour average and the
concentration should not exceed 0.13
jig/1 at any time,
TDE
The available data for TDE indicate
that acute toxicity to saltwater aquatic
life occurs at concentrations as low as
3.6 jig/1 and would occur at lower
concentrations among species that are
more sensitive than those tested. No
data are available concerning the
chronic toxicity of TDE to sensitive
saltwater aquatic life.
DDE
The available data for DDE indicate
that acute toxicity to saltwater aquatic
life occurs at concentrations as low as
14 fig/1 and would occur at lower
concentrations among species that are
more sensitive than those tested. No
data are available concerning the
chronic toxicity of DDE to sensitive
saltwater aquatic life.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of DDT through
ingestion of contaminated water and
contaminated aquatic organisms, the
ambient water concentration should be
zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk over the lifetime are
estimated at 10"s, 10"', and 10~7. The
corresponding criteria are .24 ng/1, .024
ng/1. and .0024 ng/1, respectively. If the
above estimates are made for
consumption of aquatic organisms only,
excluding consumption of water, the
levels are .24 ng/1, .024 ng/1, and .0024
ng/1, respectively. Other concentrations
. representing different risk levels may be
calculated by use of the Guidelines. The
risk estimate range is presented for
information purposes and does not
represent an Agency judgment of an
"acceptable" risk level.
Dichlorobenzeaes
Freshwater Aquatic Life
The available data for
dichlorobenzenes indicate that acute
and chronic toxicity to freshwater
aquatic life occurs at concentrations as
low as 1,120 and 763 fig/1, respectively,
and would occur at lower
concentrations among species that are
more sensitive than those tested.
Saltwater Aquatic Life
The available data for
dichlorobenzenes indicate that acute
toxicity to saltwater aquatic life occurs
at concentrations as low as 1,970 fig/1
and would occur at lower
concentrations among species that are
more sensitive than those tested. No
data are available concerning the
chronic toxicity of dichlorobenzenes to
sensitive saltwater aquatic life.
Human Health
For the protection of human health
from the toxic properties of
dichlorobenzenes (all isomers) ingested
through water and contaminated aquatic
organisms, the ambient water criterion
is determined to be 400 fig/1.
For the protection of human health
from the toxic properties of
dichlorobenzenes (all isomers) ingested
.through contaminated aquatic organisms
alone, the ambient water criterion is
determined to be 2.6 mg/1.
Dichlorobenzidines
Freshwater Aquatic Life
The data base available for
dichlorobenzidines and freshwater
organisms is limited to one test on
bioconcentration of 3,3'-
dichlorobenzicline and no statement can
be made concerning acute or chronic
toxicity.
210
-------
Saltwater Aquatic Life
No saltwater organisms have been
tested with any dichlorobenzidine and
no statement can be made concerning
acute or chronic toxicity.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of
dichlorobenzidine through ingestion of
contaminated water and contaminated
aquatic organisms, the ambient water
concentration should be zero base on
the non-threshold assumption for this
chemical. However, zero level may not
be attainable at the present time.
Therefore, the levels which may result in
incremental increase of cancer risk over
the lifetime are estimated at 10"*, 10"*,
and 10~7. The corresponding criteria are
.103 tig/I .0103 fig/1, and .00103 fig/1.
respectively. If the above estimates are
made for consumption of aquatic
organisms only, excluding consumption
of water, the levels are .204 jig/1, -0204
fig/1, and .00204 ftg/1, respectively.
Other concentrations representing
different risk levels may be calculated
by use of the Guidelines. The risk
estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level.
Dichloroethylenes
Freshwater Aquatic Life
The available data for
dichloroethylenes indicate that acute
toxicity to freshwater aquatic life occurs
at concentrations as low as 11,600 jig/I
and would occur at lower
concentrations among species that are
more sensitive than those tested. No
definitive data are available concerning
the chronic toxicity of dlchlorethylenea
to sensitive freshwater aquatic life.
Saltwater Aquatic Life
The available data for
dichlorethylenes indicate that acute
toxicity to saltwater aquatic life occurs
at concentrations as low as 224,000 ng/\
and would occur at lower
concentrations among species that are
more sensitive than those tested. No
data are available concerning the
chronic toxicity dichloroethylenes to
sensitive saltwater aquatic life.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of
1.1 -dir.hloroethylene through ingestion of
contaminated water and contaminated
aquatic organisms, the ambient water
concentration should be zero based on
the non-threshold assumption for this
chemical. However, zero level may not
be attainable at the present time.
Therefore, the levels which may result in
incremental increase of cancer risk over
the lifetime are estimated at 10"*, 10"*,
and 10"'. The corresponding criteria are
.33 jig/1, .033 jig/1, and .0033 jig/1,
respectively. If the above estimates are
made for consumption of aquatic
organisms only, excluding consumption
of water, the levels are 1B.5 fig/1.1.85
fig/1, and .IBS jig/1, respectively. Other
concentrations representing different
risk levels may be calculated by use of
the Guidelines. The risk estimate range
is presented for information purposes
and does not represent an Agency
judgment on an "acceptable" risk level.
Using the present guidelines, a
satisfactory criterion cannot be derived
at this time due to the insufficency in the
available data for 1,2-dichloroethylene.
2,4-Dichloropbenol
Freshwater Aquatic Life
The available data for 2,4-
dichlorophenol indicate that acute and
chronic toxicity .to freshwater aquatic
life occurs at concentrations as low as
2,020 and 365 jig/1, respectively, and
would occur at lower concentrations
among species that are more sensitive
that those tested. Mortality to early life
stages of one species of fish occurs at
concentrations as low as 70 jtg/1,
Saltwater Aquatic Life
Only one test has been conducted
With saltwater organisms on 2,4-
dichlorophenol and no statement can be
made concerning acute or chronic
toxicity.
Human Health
For comparison purposes, two
approaches were used to derive
criterion levels for 2,4-dichlorophenol.
Based on available toxicity data, for the
protection of public health, the derived
level is 3.09 mg/1. Using available
organoleptic data, for controlling
undesirable taste and odor quality of
ambient water, the estimated level is 0.3
jig/1. It should be recognized that
organoleptic data as a basis for
establishing a water quality criteria
have limitations and have no
demonstrated relationship to potential
adverse human health effects.
Dichloropropanes/Dichloropropenes
freshwater Aquatic Life
The available data for
dichloropropanes indicate that acute
and chronic toxicity to freshwater
aquatic life occurs at concentrations as
low as 23,000 and 5,700 jig/1,
respectively, and would occur at lower
concentrations among species that are
more sensitive than those tested.
The available data.for
dichloropropenes indicate that acute
and chronic toxicity to freshwater
aquatic life occurs at concentrations as
low as 6,060 and 244 fig/I, respectively,
and would occur at lower
concentrations among species that are
more sensitive than those tested.
Saltwater Aquatic Life
The available data for
dichloropropanes indicate that acute
and chronic toxicity to saltwater aquatic
life occurs at concentrations as low as
10,300 and 3,040 jig/1, respectively, and
would occur at lower concentrations
among species that are more sensitive
than those tested.
The available data for
dichloropropenes indicate that acute
toxicity to saltwater aquatic life occurs
at concentrations as low a as 790 fig/1,
and would occur at lower
concentrations among species that are
more sensitive than those tested. No
data are available concerning the
chronic toxicity of dichloropropenes to
sensitive saltwater aquatic life.
Human Health
Using the present guidelines, a
satisfactory criterion cannot be derived
at this time due to the insufficiency in
the available data for dichloropropanes.
For the protection of human health
from the toxic properties of
dichloropropenes ingested through
water and contaminated aquatic
organisms, the ambient water criterion
is determined to be 87 fig/1.
For the protection of human health
from the toxic properties of
dichloropropenes ingested through
contaminated aquatic organisms alone,
the ambient water criterion is
determined to be 14.1 mg/1.
2,4-Dimethylphenol
Freshwater Aquatic Life
The available data for 2,4-
dimethylphenol indicate that acute
toxicity to freshwater aquatic life occurs
at concentrations as low as 2,120 jig/1
and would occur at lower
concentrations among species that are
more sensitive than those tested. No
data are available concerning the
chronic toxicity of dimethylphenol to
sensitive freshwater aquatic life.
Saltwater Aquatic Life
211
-------
No saltwater organisms have been
tested with 2,4-dimethylphenol and no
statement can be made concerning acute
and chronic toxicity.
Human Health
Sufficient data are not available for
2,4-dimethylphenol to derive a level
which would protect against the
potential toxicity of this compound.
Using available organoleptic data, for
controlling undersirable taste and odor
quality of ambient water, the estimated
level is 400 fig/1. It should be recognized
that organoleptic data as a basis for
establishing a water quality criteria
have limitations and have no
demonstrated relationship to potential
adverse human health effects.
2,4-Dinitrotoluene
Freshwater Aquatic Life
The available data for 2,4-
dinitrotoluene indicate that acute and
chronic toxicity to freshwater aquatic
life occurs at concentrations as low as
330 and 230 u-g/1, respectively, and
would occur at lower concentrations
among species that are more sensitive
than those tested.
Saltwater Aquatic Life
The available data for 2,4-
dinitrotoluenes indicate that acute
toxicity to saltwater aquatic life occurs
at concentrations as low as 590 u.g/1 and
would occur at lower concentrations
among species that are more sensitive
than those tested. No data are available
concerning the chronic toxicity of 2,4-
dinitrotoluenes to sensitive saltwater
aquatic life but a decrease in algal cell
numbers occurs at concentrations as
low as 370 ng/L
Haitian Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of 2.4-
dinitrotoluene through ingestion of
contaminated water and contaminated
aquatic organisms, the ambient water
concentration should be zero based on
the non-threshold assumption for this
chemical. However, zero level may not
be attainable at the present time.
Therefore, the levels which may result in
incremental increase of cancer risk over
the lifetime are estimated at 10~5,10~8,
and 10"'. The corresponding criteria are
1.1 ug/1, 0.11 ug/1, and 0.011 fig/1,
respectively. If the above estimates are
made for consumption of aquatic
organisms only, excluding consumption
of water, the levels are 91 fig/I, 9.1 fig/1,
and 0.91 ug/1, respectively. Other
concentrations representing different
risk levels may be calculated by use of
the Guidelines. The risk estimate range
is presented for information purposes
and does not represent an Agency
judgment on an "acceptable" risk level.
1,2-Diphenylhydrazine'
Freshwater Aquatic Life
The available data for 1,2-
diphenylhydrazine indicate that acute
toxicity to freshwater aquatic life occurs
at concentrations as low as 270 fig/1 and
would occur at lower concentrations
among species that are more sensitive
than those tested. No data are available
concerning the chronic toxicity of 1,2-
diphenylhydrazine to sensitive
freshwater aquatic life.
Saltwater Aquatic Life
No saltwater organisms have been
tested with 1,2-diphenylhydrazine and
no statement can be made concerning
acute and chronic toxicity.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of 1,2-
diphenylhydrazine through ingestion of
contaminated water and contaminated
aquatic organisms, the ambient water
concentration should be zero based on
the non-threshold assumption for this
chemical. However, zero level may not
be attainable at the present time.
Therefore, the levels which may result in
incremental increase of cancer risk over
the lifetime are estimated at 10"s, 10" ',
and 10"'. The corresponding criteria are
422 ng/1, 42 ng/1, and 4 ng/1,
respectively. If the above estimates are
made for consumption of aquatic
organisms only, excluding consumption
of water, the levels are 5.6 u.g/1, 0.56
fig/1, and O.OS8 fig/1, respectively.
Other concentrations representing
different risk levels may be calculated
by use of the Guidelines. The risk
estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level.
Endosulfan
Freshwater Aquatic Life
For endosulfan the criterion to protect
freshwater aquatic life as derived using
the Guidelines is 0.056 fig/I as a 24-hour
average and the concentration should
not exceed 0.22 fig/1 at any time.
Saltwater Aquatic Life
For endosulfan the criterion to protect
saltwater aquatic life as derived using
the Guidelines is 0.0087 fig/1 as a 24-
hour average and the concentration
should not exceed 0.034 fig/1 at any
time.
Human Health
For the protection of human health
from the toxic properties of endosulfan
ingested through water and
contaminated aquatic organisms, the
ambient water criterion is determined to
be 74 jig/1.
For the protection of human health
from the toxic properties of endosulfan
ingested through contaminated aquatic
organisms alone, the ambient water
criterion is determined to be 159 fig/1.
Endrin
Freshwater Aquatic Life
For endrin the criterion to protect
freshwater aquatic life as derived using
the Guidelines is 0.0023 fig/1 as a 24-
hour average and the concentration
should not exceed 0.18 u.g/1 at any time.
Saltwater Aquatic Life
For endrin the criterion to protect
saltwater aquatic life as derived using
the Guidelines is 0.0023 u.g/1 as a 24-
hour average and the concentration
should not exceed 0.037 fig/1 at any
time.
Human Health
The ambient water quality criterion
for endrin is recommended to be
identical to the existing drinking water
standard which is 1 fig/1. Analysis of the
toxic effects data resulted in a
calculated level which is protective of
human health against the ingestion of
contaminated water and contaminated
aquatic organisms. The calculated value
is comparable lo the present standard.
For this, reason a selective criterion
based on exposure solely from
consumption of 6.5 grams of aquatic
organisms was not derived.
Ethylbenzene
Freshwater Aquatic Life
The available data for ethylbenzene
indicate that acute toxicity to freshwater
aquatic life occurs at concentrations as
low as 32,000 ug/1 and would occur at
lower concentrations among species
that are more sensitive than those
tested. No definitive data are available
concerning the chronic toxicity of
ethylbenzene to sensitive freshwater
aquatic life.
Saltwater Aquatic Life
The available data for ethylbenzene
indicate that acute toxicity to saltwater
aquatic life occurs at concentrations as
low as 430 fig/1 and would occur at
lower concentrations among species
that are more sensitive than those
tested. No data are available concerning
the chronic toxicity of ethylbenzene to
sensitive saltwater aquatic life.
212
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Human Health
For the protection of human health
from the toxic properties of
ethylbenzene ingested through water
and contaminated aquatic organisms,
the ambient water criterion is
determined to be 1.4 mg/1.
For the protection of human health
from the toxic properties of
ethylbenzene ingested through
contaminated aquatic organisms alone.
the ambient water criterion is
determined to be 3.28 mg/1.
Fluoranthene
Freshwater Aquatic Life
The available data for fluoranthene
indicate that acute toxicity to freshwater
aquatic life occurs at concentrations as
low as 3980 fig/1 and would occur at
lower concentrations among species
that are more sensitive than those
tested. No data are available concerning
the chronic toxicity of fluoranthene to
sensitive freshwater aquatic life.
Saltwater Aquatic Life
The available data for fluoranthene
indicate that acute and chronic toxicity
to saltwater aquatic life occur at
concentrations as low as 40 and 16 fig/1,
respectively, and would occur at lower
concentrations among species that are
more sensitive than those tested.
Human Health
For the protection of human health
from the toxic properties of fluoranthene
ingested through water and
contaminated aquatic organisms, the
ambient water criterion is determined to
be 42 ug/1.
For the protection of human health
from the toxic properties of fluoranthene
ingested through contaminated aquatic
organisms alone, the ambient water
criterion is determined to be 54 fig/l.
Haloe there
Freshwater Aquatic Life
The available data for haloethers
indicate that acute and chronic toxicity
to freshwater aquatic life occur at
concentrations as low as 360 and 122
fig/1, respectively, and would occur at
lower concentrations among species
that are more sensitive than those
tested.
Saltwater Aquatic Life
No saltwater organisms have been
tested with any haloether and no
statement can be made concerning acute
or chronic toxicity.
Human Health
Using the present guidelines, a
satisfactory criterion cannot be derived
at this time due to the insufficiency in
the available data for haloethers.
Halomethanes
Freshwater Aquatic Life
The available data for halomethanes
indicate that acute toxicity to freshwater
aquatic life occurs at concentrations as
low as 11,000 fig/1 and would occur at
lower concentrations among species
that are more sensitive than those
tested. No data are available concerning
the chronic toxicity of halomethanes to
sensitive freshwater aquatic life.
Saltwater Aquatic Life
The available data for halomethanes
indicate that acute and chronic toxicity
to saltwater aquatic life occur at
concentrations as low as 12,000 and
6,400 /ig/1. respectively, and would
occur at lower concentrations among
species that are more sensitive than
those tested. A decrease in algal cell
numbers occurs at concentrations as
low as 11,500 fig/1.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of
chloromethane, bromomethane,
dichloromethane,
bromodichlorome thane,
tribromomethane,
dichlorodifluoromethane,
trichlorofluoromethane, or combinations
of these chemicals through ingestion of
contaminated water and contaminated
aquatic organisms, the ambient water
concentration should be zero based on
the non-threshold assumption for this
chemical. However, zero level may not
be attainable at the present time.
Therefore, the levels which may result in
incremental increase of cancer risk, over
the lifetimes are estimated at 10"*, 10"',
and 10"7. The corresponding criteria are
1.9 fig/1, 0.19 jig/1, and 0.019 fig/1,
respectively. If the above estimates are
made for consumption of aquatic
organisms only, excluding consumption
of water, the levels are 157 /ig/1,15.7
fig/1, and 1.57 fig/1, respectively. Other
concentrations representing different
risk levels may be calculated by use of
the Guidelines. The risk estimate range
is presented for information purposes
and does not represent an Agency
judgment on an "acceptable" risk level.
Heptachlor
Freshwater Aquatic Life
For heptachlor the criterion to protect
freshwater aquatic life as derived using
the Guidelines is 0.0038 fig/1 as a 24-
hour average and the concentration
should not exceed 0.52 fig/1 at any time.
Saltwater Aquatic Life
For heptachlor the criterion to protect
saltwater aquatic life as derived using
the Guidelines is 0.0036 fig/1 as a 24-
hour average and the concentration
should not exceed 0.053 fig/1 at any
time.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of heptachlor
through ingestion of contaminated water
and contaminated aquatic organisms,
the ambient water concentration should
be zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk, over the lifetimes are
estimated at 10" • 10" • and 10~7. The
corresponding criteria are 2.78 ng/1, .28
ng/1, and .028 ng/1, respectively. If the
above estimates are made for
consumption of aquatic organisms only,
excluding consumption of water, the
levels are 2.65 ng/1, .29 ng/1, and .029
ng/1, respectively. Other
concentrations representing different
risk leveis may be calculated by use of
the Guidelines. The risk estimate range
is presented for information purposes
and does not represent an Agency
judgment on an "acceptable" risk level.
Hexachlorobutadiene
Fresh water Aquatic Life
The available data for
hexachlorobutadiene indicate that acute
and chronic/toxicity to freshwater
aquatic life occur at concentrations as
low as 90 and 9.3 fig/1, respectively, and
would occur at lower concentrations
among species that are more sensitive
than those tested.
Saltwater Aquatic Life
The available data for
hexachlorobutadiene indicate that acute
toxicity to saltwater aquatic life occurs
at concentrations as low as 32 fig/I and
would occur at lower concentrations
among species that are more sensitive
that those tested. No data are available
concerning the chronic toxicity of
hexachlorobutadiene to sensitive
saltwater aquatic life
Human Health
213
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For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of
hexachlorobutadiene through ingestion
of contaminated water and
contaminated aquatic organisms, the
ambient water concentration should be
zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk, over the lifetimes are
estimated at 10's, 10"g, and 10"', The
corresponding criteria are 4,47 fig/1, 0.45
fig/1, and 0.045 fig/1, respectively. If the
above estimates are made for
consumption of aquatic organisms only,
excluding consumption of water, the
levels are 500 |ig/l, 50 fig/1, and § fig/1
respectively. Other concentrations
representing different risk levels may be
calculated by use of the Guidelines. The
-risk estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level.
Hexachlorocyclohexane
Lindane
Freshwater Aquatic Life
For Lindane the criterion to protect
freshwater aquatic life as derived using
the Guidelines is 0.080 fig/1 as a 24-hour
average and the concentration should
not exceed 2,0 fig/1 at any time.
Saltwater Aquatic Life
For saltwater aquatic life the
concentration of lindane should not
exceed 0.16 fig/1 at any time. No data
are available concerning the chronic
toxicity of lindane to sensitive saltwater
aquatic life.
BHC
Freshwater Aquatic Life
The available date for a mixture of
isomers of BHC indicate that acute
toxicity to freshwater aquatic life occurs
at concentrations as low as 100 fig/1 and
would occur at lower concentrations
among species that are more sensitive
than those tested. No data are available
concerning the chronic toxicity of a
mixture of isomers of BHC to sensitive
freshwater aquatic life.
Saltwater Aquatic Life
The available date for a mixture of
isomers of BHC indicate that acute
toxicity to saltwater aquatic life occurs
at concentrations as low as 0.34 fig/1
and would occur at lower
concentrations among species that are
more sensitive than those tested. No
data are available concerning the
chronic toxiciiy of a mixture of isomers
of BHC to sensitive saltwater aquatic
life.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of alpha-HCH
through ingestion of contaminated water
and contaminated aquatic organisms,
the ambient water concentration should
be zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk, over the lifetimes are
estimated at 10~5,10~s, and 10"'. The
corresponding criteria are 92 ng/1, 9.2
ng/1, and .92 ng/1, respectively. If (he
above estimates are made for
consumption of aquatic organisms only,
excluding consumption of water, the
levels are 310 ng/1, 31,0 ng/1, and 3.1
ng/1 respectively. Other concentrations
representing different risk levels may be
calculated by use of the Guidelines. The
risk estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level.
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of beta-HCH
through ingestion of contaminated water
and contaminated aquatic organisms,
the ambient water concentration should
be zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk, over the lifetimes are
estimated at 10"*, 10~ •, and 10"'. The
corresponding criteria are 163 ng/1,16.3
ng/I, and 1.63 ng/1, respectively. If the
above estimates are made for
consumption of aquatic organisms only,
excluding consumption of water, the
levels are 547 ng/1, 54.7 ng/1, and 5.47
ng/1, respectively. Other concentrations
representing different risk levels may be
calculated by use of the Guidelines. The
risk estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level.
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of tech-HCH
through ingestion of contaminated water
and contaminated aquatic organisms,
the ambient water concentration should
be zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk, over the lifetimes are
estimated at 10"s, 10~«, and 10"*. The
corresponding criteria are 123 ng/1,12.3
ng/1, and 1.23 ng/1, respectively. If the
above estimates are made for
consumption of aquatic organisms only,
excluding consumption of water, the
levels are 414 ng/1, 41.4 ng/1, and 4.14
ng/1, respectively. Other concentrations
representing different risk levels may be
calculated by use of the Guidelines. The
risk estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level.
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of gamma-HCH
through ingestion of contaminated water
and contaminated aquatic organisms,
the ambient water concentrations
should be zero based on the non-
threshold assumption for this chemical.
However, zero level may not be
attainable at the present time.
Therefore, the levels which may result in
incremental increase of cancer risk over
the lifetime are estimated at 10"5,10"*,
and 10"'. The corresponding criteria are
186 ng/1,18.6 ng/1. and 1.86 ng/1,
respectively. If the above estimates are
made for consumption of aquatic
organisms only, excluding consumption
of water, the levels are 625 ng/1, 62.5
ng/1, 6.25 ng/1, respectively. Other
concentrations representing different
risk levels may be calculated by use of
the Guidelines. The risk estimate range
is presented for information purposes
and does not represent an Agency
judgment on an "acceptable" risk level.
Using the present guidelines, a
satisfactory criterion cannot be derived
at this time due to the insufficiency in
the available data for delta-HCH.
Using the present guidelines, a
satisfactory criterion cannot be derived
at this time due to the insufficiency in
the available data for epsilon-HCH.
Hexachlorocyclopentadiene
Freshwater Aquatic Life
The available data for
hexachlorocyclopentadiene indicate that
acute and chronic toxicity to freshwater
aquatic life occurs at concentrations as
low as 7.0 and 5.2 fig/1, respectively, and
would occur at lower concentrations
among species that are more sensitive
than those tested,
Saltwater Aquatic Life
The available data to
hexachlorocyclopentadiene indicate that
acute toxicity to saltwater aquatic life
occurs at concentrations as low as 7.0
ftg/1 and would occur at lower
concentration:) among species that are
214
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more sensitive than those tested. No
data are available concerning the
chronic toxicity of
hexachlorocyclopentadiene to sensitive
saltwater aquatic life.
Human Health
For comparison purposes, two
approaches were used to derive
criterion levels for
hexachlorocyclopentadiene. Based on
available toxicity data, for the
protection of public health, the derived
level is 206 fig/1. Using available
organoleptic data, for controlling
undesirable taste and odor quality of
ambient water, the estimated level is 1.0
fig/1. It should be recognized that
organoleptic data as a basis for
establishing a water quality criterion
have limitations and have no
demonstrated relationship to potential
adverse human health effects.
Isophorone
Freshwater Aquatic Life
The available data for isophorone
indicate that acute toxicity to freshwater
aquatic life ocurs at concentrations as
low as 117,000 fig/1 and would occur at
lower concentrations among species
that are more sensitive than those
tested. No data are available concerning
the chronic toxicity of isophorone to
sensitive freshwater aquatic life.
Saltwater Aquatic Life
The available data for isophorone
indicate that acute toxicity to saltwater
aquatic life occurs at concentrations as
low as 12,900 fig/1 and would occur at
lower concentrations among species
that are more sensitive than those
tested. No data are available concerning
the chronic toxicity of isophorone to
sensitive saltwater aquatic life.
Human Health
For the protection of human health
from the toxic properties of isophorone
ingested through water and
contaminated aquatic organisms, the
ambient water criterion is determined to
be 5.2 mg/1.
For the protection of human health
from the toxic properties of isophorone
ingested through contaminated aquatic
organisms alone, the ambient water
criterion is determined to be 520 mg/1.
Lead
Freshwater Aquatic Life
For total recoverable lead the
criterion (in fig/1) to protect freshwater
aquatic life as derived using the
Guidelines is the numerical value given
by e(2.35[ln(hardness)]-9.48) as a 24-
hour average and the concentration (in
fig/1) should not exceed the numerical
value given by e(1.22[ln(hardness)]-0.47)
at any time. For example, at hardnesses
of 50,100, and 200 mg/1 as CaCO, the
criteria are 0.75, 3.8, and 20 fig/1,
respectively, as 24-hour averages, and
the concentrations should not exceed 74,
170, and 400 ftg/1, respectively, at any
time.
Saltwater Aquatic Life
The available data for total
recoverable lead indicate that acute and
chronic toxicity to saltwater aquatic life
occur at concentrations as low as 668
and 25 fig/1, respectively, and would
occur at lower concentrations among
species that are more sensitive than
those tested.
Human Health
The ambient water quality criterion
for lead is recommended to be identical
to the existing drinking water standard
which is 50 fig/1. Analysis of the toxic
effects data resulted in a calculated
level which is protective to human
health against the ingestion of
contaminated water and contaminated
aquatic organisms. The calculated value
is comparable to the present standard.
For this reason a selective criterion
based on exposure solely from
consumption of 6.5 grams of aquatic
organisms was not derived.
Mercury
Freshwater Aquatic Life
For total recoverable mercury the
criterion to protect freshwater aquatic
life as derived using the Guidelines is
0.00057 fig/1 as a 24-hour average and
the concentration should not exceed
0.0017 fig/1 at any time.
Saltwater Aquatic Life
For total recoverable mercury the
criterion to protect saltwater aquatic life
as derived using the Guidelines is 0.025
fig/1 as a 24-hour average and the
concentration should not exceed 3.7 fig/1
at any time.
Human Health
For the protection of human health
from the toxic properties of mercury
ingested through water and
contaminated aquatic organisms, the
ambient water criterion is determined to
be 144 ng/1.
For the protection of human health
from the toxic properties of mercury
ingested through contaminated aquatic
organisms alone, the ambient water
criterion is determined to be 146 ng/1.
Note.—These values include the
consumption of freshwater, estuarine, and
marine species.
Naphthalene
Freshwater Aquatic Life
The available data to naphthalene
indicate that acute and chronic toxicity
to freshwater aquatic life occur at
concentrations as low as 2,300 and 620
fig/1, respectively, and would occur at
lower concentrations among species
that are more sensitive than those
tested.
Saltwater Aquatic Life
The available data for naphthalene
indicate that acute toxicity to saltwater
aquatic life occurs at concentrations as
low as 2,350 fig/1 and would occur at
lower concentrations among species
that are more sensitive than those
tested. No data are available concerning
the chronic toxicity of naphthalene to
sensitive saltwater aquatic life.
Human Health
Using the present guidelines, a
satisfactory criterion cannot be derived
at this time due to the insufficiency in
the available data for naphthalene.
Nickel
Freshwater Aquatic Life
For total recoverable nickel the
criterion (in fig/1) to protect freshwater
aquatic life as derived using the i,
Guidelines is the numerical value given
by e(0.76 [In (hardness)] +1.06) as a 24-
hour average and the concentration (in
fig/1) should not exceed the numerical
value given by e(0.76[ln (hardness)] ~f-
4.02) at any time. For example, at
hardnesses of 50,100, and 200 mg/1 as
CaCOj the criteria are 56, 96, and 160
fig/1, respectively, as 24-hour averages,
and the concentrations should not
exceed 1,100,1.800, and 3,100 fig/1,
respectively, at any time.
Saltwater Aquatic Life
For total recoverable nickel the
criterion to protect saltwater aquatic life
as derived using the Guidelines is 7.1
fig/1 as a 24-hour average and the
concentration should not exceed 140 fig/
1 at any time.
Human Health
For the protection of human health
from the toxic properties of nickel
ingested through water and
contaminated aquatic organisms, the
ambient water criterion is determined to
be 13.4 fig/1.
For the protection of human health
from the toxic properties of nickel
ingested through contaminated aquatic
organisms alone, the ambient water
criterion is determined to be 100 fig/1.
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Nitrobenzene
Freshwater Aquatic Life
The available data for nitrobenzene
indicate that acute toxicity to freshwater
aquatic life occurs at concentrations as
low as 27,000 fig/1 and would occur at
lower concentrations among species
that are more sensitive than those
tested. No definitive data are available
concerning the chronic toxicity of
nitrobenzene to sensitive freshwater
aquatic life,
Saltwater Aquatic Life
The available data for nitrobenzene
indicate that acute toxicity to saltwater
aquatic life occurs at concentrations as
low as 6,680 |ig/l and would occur at
lower concentrations among species
that are more sensitive than those
tested. No data are available concerning
the chronic toxicity of nitrobenzene to
sensitive saltwater aquatic life.
Human Health
For comparison purposes, two
approaches were used to derive
criterion levels for nitrobenzene. Based
on available toxicity data, for the
protection of public health, the derived ,
level is 19,8 rag/1. Using available
organoleptic data, for controlling
undesirable taste and odor quality of
ambient water, the estimated level is 30
fig/l. It should be recognized that
organoleptic data as a basis for
establishing a water quality criteria
have limitations and have no
demonstrated relationship to potential
adverse human health effects.
Nitrophenols
Freshwater Aquatic Life
The available data for nitrophenols
indicate that acute toxicity to freshwater
aquatic life occurs at concentrations as
low as 230 fig/1 and would occur at
tower concentrations among species
that are more sensitiva than those
tested. No data are available concerning
the chronic toxicity of nitrophenols to
sensitive freshwater aquatic life but
toxicity to one species of algae occurs at
concentrations as low as ISO ng/I.
Saltwater Aquatic Life
The available data for nitrophenols
indicate that acute toxicity to saltwater
aquatic life occurs at concentrations as
low as 4,850 fig/1 and would occur at
lower concentrations among species
that are more sensitive than those
tested. No data are available concerning
the chronic toxicity of nitrophenols to
sensitive saltwater aquatic life.
Human Health
For the protection of human health
from the toxic properties of 2,4-dinitro-o-
cresol ingested through water and
contaminated aquatic organisms, the
ambient water criterion is determined to
be 13.4 jig/1.
For the protection of human health
from the toxic properties of 2.4-dinitro-o-
cresol ingested through contaminated
aquatic organisms alone, the ambient
water criterion is determined to be 765
M5/1.
For the protection of human health
from the toxic properties of
dinitrophenoi ingested through water
and contaminated aquatic organisms,
the ambient water criterion is
determined to be 70 jug/!,
For the protection of human health
from the toxic properties of
dinitrophenoi ingested through
contaminated aquatic organisms alone,
the ambient water criterion is
determined to be 14.3 mg/1.
Using the present guidelines, a
satisfactory criterion cannot he derived
at this time due to the insufficiency in
the available data for mononitrophenol.
Using the present guidelines, a
satisfactory criterion cannot be derived
at this time due to the insufficiency in
the available data for Iri-nitrophenol.
Nitrosamines
Freshwater Aquatic Life
The available data for nitrosamines
indicate that acute toxicity to freshwater
aquatic life occurs at concentrations as
low as 5.85O (Ag/1 and would occur at
lower concentrations among species
that are more sensitive than those
tested. No data are available concerning
the chronic toxicity of nitrosamines to
sensitive freshwater aquatic life.
Saltwater Aquatic Life
The available data for nitrosamines
indicate that acute toxicity to saltwater
aquatic life occurs at concentrations as
low as 3,300,000 jig/1 and would occur at
lower concentrations among species
that are more sensitive than those
tested. No data are available concerning
the chronic toxicity of nitrosamines to
sensitive saltwater aquatic life.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of n-
nitrosodimethylamine through ingestion
of contaminated water and
contaminated aquatic organisms, the
ambient water concentration should be
zero based on ths non-threshold
assumption for this chemical. However,
zero level may not be attainable af the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk, over the lifetimes are
estimated at 10-", 10"*, and 10"', The
corresponding criteria are 14 ng/1,1.4
ng/1, and .14 ng/1, respectively. If the
above estimates are made for
consumption of aquatic organisms only,
excluding consumption of water, the
levels are 160,000 ng/1,16,000 ng/1, and
1,600 ng/1, respectively. Other
concentrations representing different
risk levels may be calculated by use of
the Guidelines. The risk estimate range
is presented for information purposes
and does not represent an Agency
judgment on an "acceptable" risk level.
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of n-
nitrosodiethylamine through ingestion of
contaminated water and contaminated
aquatic organisms, the ambient water
concentration should be zero based on
the non-threshold assumption for this
chemical. However, zero level may not
be attainable at the present time.
Therefore, the levels which may result in
Incremental increase of cancer risk, over
the lifetimes are estimated at 10~s, 10"",
and 10"'. The corresponding criteria are
8 ng/1,0.8 ng/1, and 0.08 ng/1,
respectively. If the above estimates are
made for consumption of aquatic
organisms only, excluding consumption
of water, the levels are 12,400 ng/1,1,240
ng/1, and 124 ng/1, respectively. Other
concentrations representing different
risk levels may be calculated by use of
the Guidelines. The risk estimate range
is presented for information purposes
and does not represent an Agency
judgment on an "acceptable" risk level.
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure in n-nitrosodi-n-
butylamine through ingestion of
contaminated water and contaminated
aquatic Organisms, the ambient water
concentration should be zero based on
the non-threshold assumption for this
chemical. However, zero level may not
be attainable at the present time.
Therefore, the levels which may result in
incremental increase of cancer risk, over
the lifetimes are estimated at 10" 8,10"*,
and 10~7. The corresponding criteria are
64 ng/16.4 ng/1 and .064 ng/1,
respectively. If the above estimates are
made for consumption of aquatic
organisms only, excluding consumption
of water, the levels are 5,868 ng/1, 587
ng/1, and 58.7 ng/1, respectively. Other
concentrations representing different
216
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risk levels may be calculated by use of
the Guidelines. The risk estimate range
is presented for information purposes
and does not represent an Agency
judgment on an "acceptable" risk level.
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure in n-
nitrosodiphenylamine through ingestion
of contaminated water and
contaminated aquatic organisms, the
ambient water aoncentration should be
zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk, over the lifetimes are
estimated at 10" 5, 10" • and 10"'. The
corresponding criteria are 49,000 ng/1
4,900 ng/1 and 490 ng/1, respectively. If
the above estimates are made for
consumption of aquatic organisms only,
excluding consumption of water, the
levels are 161,000 ng/1,16,100 ng/1, and
1,610 ng/1, respectively. Other
concentrations representing different
risk levels may be calculated by use of
the Guidelines. The risk estimate range
is presented for information purposes
and does not represent an Agency
judgment on an "acceptable" risk level.
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure in n-
nitrosopyrrolidine through ingestion of
contaminated water and contaminated
aquatic organisms, the ambient water
concentration should be zero based on
the non-threshold assumption for this
chemical. However, zero level may not
be attainable at the present time.
Therefore, the levels which may result in
incremental increase of cancer risk, over
the lifetimes are estimated at W', 10" •
and 10"7. The corresponding criteria are
160 ng/116.0 ng/1 and 1.60 ng/1,
respectively. If the above estimates are
made for consumption of aquatic
organisms only, excluding consumption
of water, the levels are 919,000 ng/1,
91,900 ng/1, and 9,190 ng/1, respectively.
Other concentrations representing
different risk levels may be calculated
by use of the Guidelines. The risk
estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level.
Pentfichlorophenol
Freshwater Aquatic Life
The available data for
pentachlorophenol indicate that acute
and chronic toxicity to freshwater
aquatic life occur at concentrations as
low as 55 and 3.2 p.g/1, respectively, and
would occur at lower concentrations
among species that are more sensitive
than those tested.
Saltwater Aquatic Life
The available data for
pentachlorophenol indicate that acute
and chronic toxicity to saltwater aquatic
life occur at concentrations as low as 53
and 34 fig/1, respectively, and would
occur at lower concentrations among
species that are more sensitive than
those tested.
Human Health
For comparison purposes, two
approaches were used to derive
criterion levels for pentachlorophenol.
Based on available toxicity data, for the
protection of public health, the derived
level is 1.01 mg/1. Using available
organoleptic data, for controlling
undesirable taste and odor quality of
ambient water, the estimated level is 30
Hg/1. It should be recognized that
organoleptic data as a basis for
establishing a water quality criterion
have limitations and have no
demonstrated relationship to potential
adverse human health effects.
Phenol
Freshwater Aquatic Life
The available data for phenol indicate
that acute and chronic toxicity to
freshwater aquatic life occur at
concentrations as low as 10,200 and
2,560 jug/1, respectively, and would
occur at lower concentrations among
species that are more sensitive than
those tested.
Saltwater Aquatic Life
The available data for phenol indicate
that acute toxicity to saltwater aquatic
life occurs at concentrations as low as
5,800 ug/1 and would occur at lower
concentrations among species that are
more sensitive than those tested. No
data are available concerning the
chronic toxicity of phenol to sensitive
saltwater aquatic life.
Human Health
For comparison purposes, two
approaches were used to derive
criterion levels for phenol. Based on
available toxicity data, for the
protection of public health, the derived
level is 3.5 mg/1. Using available
organoleptic data, for controlling
undesirable taste and odor quality of
ambient water, the estimated level is 0.3
mg/1. It should be recognized that
organoleptic data as a basis for
establishing a water quality criterion
have limitations and have no
demonstrated relationship to potential
adverse human health effects.
Phthalate Esters
Freshwater Aquatic Life
The available data for phthalate
esters indicate that acute and chronic
toxicity to freshwater aquatic life occur
at concentrations as low as 940 and 3
f.g/1, respectively, and would occur at
lower concentrations among species
that are more sensitive than those
tested.
Saltwater Aquatic Life
The available data for phthalate
esters indicate that acute toxicity to
saltwater aquatic life occurs at
concentrations as low as 2944 fig/1 and
would occur at lower concentrations
among species that are more sensitive
than those tested. No data are available
concerning the chronic toxicity of
phthalate esters to sensitive saltwater
aquatic life but toxicity to one species of
algae occurs at concentrations as low as
3.4
Human Health
For the protection of human health
from the toxic properties of dimethyl-
phthalate ingested through water and
contaminated aquatic organisms, the
ambient water criterion is determined to
be 313 mg/1.
For the protection of human health
from the toxic properties of dimethyl-
phthalate ingested through
contaminated aquatic organisms alone,
the ambient water criterion is
determined to be 2.9 g/1.
For the protection of human health
from the toxic properties of diethyl-
phthalate ingested through water and
contaminated aquatic organisms, the
ambient water criterion is determined to
be 350 mg/1.
For the protection of human health
from the toxic properties of diethyl-
phthalate ingested through
contaminated aquatic organisms alone,
the ambient water criterion is
determined to be 1.8 g/1.
For the protection of human health
from the toxic properties of dibutyl-
phthalate ingested through water and
contaminated aquatic organisms, the
ambient water criterion is determined to
be 34 mg/1.
For the protection of human health
from the toxic properties of dibutyl-
phthalate ingested through
contaminated aquatic organisms alone,
the ambient water criterion is
determined to be 154 mg/1.
For the protection of human health
217
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from the toxic properties of di-2-
ethylhexyl-phthalate ingested through
water and contaminated aquatic
organisms, the ambient water criterion
is determined to be 15 mg/1.
For the protection of human health
from the toxic properties of di-2-
ethylhexyl-phthalate ingested through
contaminated aquatic organisms alone,
the ambient water criterion is
determined to be 50 mg/1,
Polychlorinated Biphenyls
Freshwater Aquatic Life
For polychlorinated biphenyls the
criterion to protect freshwater aquatic
iife as derived using the Guidelines is
0.014 jig/I as a 24-hour average. The
available data indicate that acute
toxicity to freshwater aquatic life
probably will only occur at
concentrations above 2,0 ftg/1 and that
the 24-hour average should provide
adequate protection against acute
toxicity,
Saltwater Aquatic Live
For polychlorinated biphenyls the
criterion to protect saltwater aquatic life
as derived using the Guidelines is 0.030
fig/1 as a 24-hour average. The available
data indicate that acute toxicity to
saltwater aquatic life probably will only
occur at concentrations above 10 fig/!
and that the 24-hour average should
provide adequate protection against
acute toxicity.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of PCBs through
ingestion of contaminated water and
contaminated aquatic organisms, the
ambient water concentration should be
zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk over the lifetime are
estimated at 1(TS, 10"6, and 19''. The
corresponding criteria are .79 ng/1, 0.79
ng/1, and .0079 ng/1, respectively. If the
above estimates are made for
consumption of aquatic organisms only,
excluding consumption of water, the
levels are .79 ng/1, .079 ng/1, and ,0079
ng/1. respectively. Other concentrations
representing different risk leveis may be
calculated by use of the Guidelines, The
risk estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level.
Polynuclear Aromatic Hydrocarbons
(PAHs)
Freshwater Aquatic Life
The limited freshwater data base
available for polynuclear aromatic
hydrocarbons, mostly from short-term
bioconcentration studies with two
compounds, does not permit a statement
concerning acute or chronic toxicity,
Saltwater Aquatic Life
The a\ailable data for polynuclear
aromatic hydrocarbons indicate that
acute toxicity to saltwater aquatic life
occurs at concentrations as low as 300
ug/1 and would occur at lower
concentrations among species that are
more sensitive than those tested. No
data are available concerning the
chronic toxicity of polynuclear aromatic
hydrocarbons to sensitive saltwater
aquatic life,
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of PAHs through
ingestion of contaminated water and
contaminated aquatic organisms, the
ambient water ooncentiation should be
zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in inerpmenlal increase of
cancer risk over the lifetime are
estimated at 1Q~S, 10"', and 10"'. The
corresponding criteria are 28 ng/1, 2.8
ng/1, and ,28 ng/I, respectively If the
above estimates are made for
consumption of aquatic organisms only.
excluding consumption of water, the
levels are 311 ng/'l, 31,1 ng/1. and 3.11
ng/1, respectively. Other concentrations
representing different risk levels may be
calculated by use of the Guidelines. The
risk estimate range is presented fur
information purposes and does not
represent an Agency judgment on an
"acceptable*" risk level.
Selenium
Freshwater Aquatic Life
For total recoverable inorganic
selenite the criterion to protect
freshwater aquatic life as derived using
the Guidelines is 35 fig/I as a 24-hour
average and the concentration should
not exceed 260 fig/1 at any time.
The available data for inorganic:
aelenate indicate that acute toxicity to
freshwater aquatic life occurs at
concentrations as low as 760 jtg/1 and
would occur at lower concentrations
among species that are more sensitive
than those tested. No data ate available
concerning the chronic toxicity of
inorganic selenate to sensitive
freshwater aquatic life.
Saltwater Aquatic Life
For total recoverable inorganic
selenite the criterion to protect saltwater
aquatic life as derived using the
Guidelines is 54 ;ig/l as a 24-hour
average and the concentration should
not exceed 410 jig/1 at any time.
No data art! available concerning the
toxicity of inorganic selenate to
saltwater aquatic life.
Human Health
The ambient water quality criterion
for selenium is recommended to be
identical to the existing drinking water
standard which is 10 fig/1. Analysis of
the toxic effects data resulted in a
calculated level which is protective of
human health against the ingestion of
contaminated water and contaminated
aquatic organisms. The calculated value
is comparable to the present standard.
For this reason a selective criterion
based on exposure solely, from
consumption of 6.5 grams of aquatic
organisms was not derived.
Silver
Freshwater Aquatic Life
For freshwater aquatic life the
concentration (to jig/1) of iota!
recoverable silver should not exceed the
numerical value given by "e[l,72(ln
(hardness)-6,52)]" at any time. For
example, at hardnesses of 50,100, 200
mg/I as CaCO* the concentration of
total recoverable silver should not
exceed 1.2, 4,1, and 13 fig/1, respectively,
al any time. The available data indicate
that chronic toxicity to freshwater
aquatic life may occur at concentrations
as low as 0.12; jig/I.
Saltwater Aquatic Life
For saltwater aquatic life the
concentration of total recoverable silver
should not exceed 2.3 fig/1 at any time.
No data are available concerning the
chronic toxicity of silver to sensitive
saltwater aquatic life.
Human Health
The ambient water quality criterion
for silver is recommended to be
identical to the existing drinking water
standard which is 50 fig/1. Analysis of
the toxic effects data resulted in a
calculated level which is protective of
human health against the ingesUon of
contaminated water and contaminated
aquatic organisms. The calculated value
ia comparable to the present standard.
21B
-------
For this reason a selective criterion
based on exposure solely from
consumption of 6.5 grams of aquatic
organisms was not derived.
Tetrachloroethylene
Freshwater Aquatic Life
The available data for
tetrachloroethylene indicate that acute
and chronic toxicity to freshwater
aquatic life occur at concentrations as
low as 5,280 and 840 p.g/1, respectively,
and would occur at lower
concentrations among species that are
more sensitive than those tested.
Saltwater Aquatic Life
The available data for
tetrachloroethylene indicate that acute
and chronic toxicity to saltwater aquatic
life occur at concentrations low as
10,200 and 450 fig/1, respectively, and
would occur at lower concentrations
among species that are more sensitive
than those tested.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of
tetrachloroethylene through ingestion of
contaminated water and contaminated
aquatic organisms, the ambient water
concentration should be zero based on
the non-threshold assumption for this
chemical. However, zero level may not
be attainable at the present time.
Therefore, the levels which may result in
incremental increase of cancer risk over
the lifetime are estimated at 10~5,10"6,
and 10"'. The corresponding criteria are
8 jig/1, ,8 fig/1, and .08 u.g/1, respectively.
If the above estimates are made for
consumption of aquatic organisms only,
excluding consumption of water, the
levels are 88.5 ftg/1, 8.85 fig/1, and .88
fig/1, respectively. Other concentrations
representing different risk levels may be
calculated by use of the Guidelines. The
risk estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level.
Thallium
Freshwater Aquatic Life
The available data for thallium
indicate that acute and chronic toxicity
to freshwater aquatic life occur at
concentrations as low as 1,400 and 40
fig/1, respectively, and would occur at
lower concentrations among species
that are more sensitive than those
tested. Toxicity to one species of fish
occurs at concentrations as low as 20
fxg/1 after 2,600 hours of exposure.
Saltwater Aquatic Life
The available data for thallium
indicate that acute toxicity to saltwater
aquatic life occurs at concentrations as
low as 2,130 fig/1 and would occur at
lower concentrations among species
that are more sensitive than those
tested. No data are available concerning
the chronic toxicity of thallium to
sensitive saltwater aquatic life.
Human Health
For the protection of human health
from the toxic properties of thallium
ingested through water and
contaminated aquatic organisms, the
ambient water criterion is determined to
be 13 fig/1.
For the protection of human health
from the toxic properties sjf thallium
ingested through contaminated aquatic
organisms alone, the ambient water
criterion is determined to be 48 fig/I.
Toluene
Freshwater Aquatic Life
The available data for toluene
indicate that acute toxicity to freshwater
aquatic life occurs at concentrations as
low as 17,500 fig/1 and would occur at
lower concentrations among species
that are more sensitive than those
tested. No data are available concerning
the chronic toxicity of toluene to
sensitive freshwater aquatic life.
Saltwater Aquatic Life
The available data for toluene
indicate that acute and chronic toxicity
to saltwater aquatic life occur at
concentrations as low as 6,300 and 5,000
fig/1, respectively, and would occur at
lower concentrations among species
that are more sensitive than those
tested.
fluman Health
For the protection of human health
from the toxic properties of toluene
ingested through water and
contaminated aquatic organisms, the
ambient water criterion is determined to
be 14.3 mg/1.
For the protection of human health
from the toxic properties of toluene
ingested through contaminated aquatic
organisms alone, the ambient water
criterion is determined to be 424 mg/1.
Toxaphene
Freshwater Aquatic Life
For toxaphene the criterion to protect
freshwater aquatic life as derived using
the Guidelines is 0.013 fig/1 as a 24-hour
average and the concentration should
not exceed 1.6 jtg/1 at any time.
Saltwater Aquatic Life
For saltwater aquatic life the
concentration of toxaphene should not
exceed 0.070 ftg/1 at any time. No data
are available concerning the chronic
toxicity of toxaphene to sensitive
saltwater aquatic life.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of toxaphene
through ingestion of contaminated water
and contaminated aquatic organisms,
the ambient water concentration should
be zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk over the lifetime are
estimated at 10"5, 10" *, and 10"'. The
corresponding criteria are 7.1 ng/1, .71
ng/'l. and .07 ng/1, respectively. If the
abqve estimates are made for
consumption of aquatic organisms only,
excluding consumption of water, the
levels are 7.3 ng/1, .73 ng/1, and .07 ng/1,
respectively. Other concentrations
representing different risk levels may be
calculated by use of the Guidelines. The
risk estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level.
Trichloroethyiene
Freshwater Aquatic Life
The available data for
trichloroethylene indicate that acute
toxicity to freshwater aquatic life occurs
at concentrations as low as 45,000 fig/1
and would occur at lower
concentrations among species that are
more sensitive than those tested. No
data are available concerning the
chronic toxicity of trichloroethylene to
sensitive freshwater aquatic life but
adverse behavioral effects occurs to one
species at concentrations as low as
21,900 fig/1.
Saltwater Aquatic Life
The available data for
trichloroethylene indicate that acute
toxicity to saltwater aquatic life occurs
at concentrations as low as 2,000 jig/1
and would occur at lower
concentrations among species that are
more sensitive than those tested. No
data are available concerning the
chronic toxicity of trichloroethylene to
sensitive saltwater aquatic life.
Human Health
For the maximum protection of human
-------
health from the potential carcinogenic
effects due to exposure of
trichloroethylene through ingestion of
contaminated water and contaminated
aquatic organisms, the ambient water
concentration should be zero based on
the non-threshold assumption for this
chemical. However, zero level may not
be attainable at the present time.
Therefore, the levels which may result in
incremental increase of cancer risk over
the lifetime are estimated at 10"*, 10"*,
and 10" *. The corresponding criteria are
27 fig/1. 2.7 f*g/l, and .27 fig/1,
respectively. If the above estimates are
made for consumption of aquatic
organisms only, excluding consumption
of water, the levels are 807 fig/1, 60.7
fig/1, and 8.07 fig/1, respectively. Other
concentrations representing different
risk levels may be calculated by use of
the Guidelines. The risk estimate range
is presented for information purposes
and does not represent an Agency
judgment on an "acceptable" risk level.
Vinyl Chloride
Freshwater Aquatic Life
No freshwater organisms have been
tested with vinyl chloride and no
statement can be made concerning acute
or chronic toxicity.
Saltwater Aquatic Life
No saltwater organisms have been
tested with vinyl chloride and no
statement can be made concerning acute
or chronic toxicity.
Human Health
For the maximum protection of human
health from the potential carcinogenic
effects due to exposure of vinyl chloride
through ingestion of contaminated water
and contaminated aquatic organisms,
the ambient water concentration should
be zero based on the non-threshold
assumption for this chemical. However,
zero level may not be attainable at the
present time. Therefore, the levels which
may result in incremental increase of
cancer risk over the lifetime are
estimated at 10~5, Hr«, and 10"'. The
corresponding criteria are 20 fig/1, 2,0
fig/1, and .2 fig/1, respectively. If the
above estimates are made for
consumption of aquatic organisms only,
excluding consumption of water, the
levels are 5,246 fig/1, 525 ftg/1, and 52.5
fig/1, respectively. Other concentrations
representing different risk levels may be
calculated by use of the Guidelines, The
risk estimate range is presented for
information purposes and does not
represent an Agency judgment on an
"acceptable" risk level.
Zinc
Freshwater Aquatic Life
For total recoverable zinc the criterion
to protect freshwater aquatic life as
derived using the Guidelines is 47 fig/1
as a 24-hour average and the
concentration (in ftg/1) should not
exceed the numerical value given by
e<»»3IIn (h.rtne»)l + I 9» aj any time. For
example, at hardnesses of 50,100, and
200 mg/1 as CaCO;i the concentration of
total recoverable zinc should not exceed
180, 320, and 570 fig/1 at any time.
Saltwater Aquatic Life
For total recoverable zinc the criterion
to protect saltwater aquatic life as
derived using the Guidelines is 58 fig/1
as a 24-hour average and the
concentration should not exceed 170 fig/
1 at any time.
Human Health
Sufficient data is not available for
zinc to derive a level which would
protect against the potential toxicity of
this compound. Using available
organoleptic data, for controlling
undesirable taste and odor quality of
ambient water, the estimated level is 5
mg/1. It should be recognized that
organoleptic data as a basis for
establishing a water quality criteria
have limitations and have not
demonstrated relationship to potential
adverse human health effects.
220
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APPENDIX C
QUALITY ASSURANCE FOR WATER SAMPLES
OVERVIEW OF QUALITY ASSURANCE PROGRAM
This Appendix summarizes the quality assurance (QA) activi-
ties and data validation procedures used for Love Canal water
analyses. The initial planning for the Love Canal project includ-
ed a comprehensive quality assurance effort/ perhaps more compre-
hensive than any previous EPA effort. Details of all of the qual-
ity assurance plans developed for the study are presented in a
four-part document entitled QualityAssurance Plan, Lgye_Canal
Study, LC-1-619-206 that was prepared by the GCA Corporation, the
primecontractorFor the project, and approved by the EPA quality
assurance officers. That document consists of a. main volume plus
Appendix A on sampling procedures, Appendix B on analytical pro-
cedures, and Appendix Q on the subcontractor's QA plans, A more
detailed discussion of the results of the prime contractor's and
subcontractor's quality assurance efforts is contained in the
Love Canal Monitoring Program, GCA QA/QCSummary Report by the
GCA Corporation. These documents, which are available through
NTIS, should be consulted for more details on the project.
The design of the water monitoring program at Love Canal and
the related quality assurance plan was developed by EPA and de-
scribed in detail in writing to the prime contractor. This writ-
ten guidance was intended to establish minimum standards for
quality assurance, and it was expected that the prime and subcon-
tractors would amplify the requirements in their individual QA
plans. During the design, study, and data evaluation phases of
the Love Canal project, the plans and results were reviewed by an
independent group, the sampling protocols study group of the
EPA's Science Advisory Board.
It was the responsibility of the prime contractor to oversee
the day-to-day quality assurance programs of the subcontractors
using the approved plans and written guidance provided by EPA.
This written guidance formed the basis for the GCA Corporation
quality assurance plan document mentioned earlier. Briefly, the
221
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written quality assurance guidance provided by EPA included the
following items:
1. Directives on sample collection, preservation, and holding
times
2. Directives on analytical methods
3. Directives on the external quality assurance program in-
cluding the use of performance evaluation samples and
quality control samples provided by EMSL-Cincinnati. The
purpose of the external quality assurance program was to
give the prime contractor some of the tools necessary to
oversee the day-to-day quality assurance program.
4. Directives on the internal quality assurance program in-
cluding required measurements of gas chromatography/mass
spectrometry (GC/MS) reference compounds, method blanks,
laboratory control standards, laboratory duplicates, sur-
rogate analytes for EPA analysis methods 624 and 625, and
known additions (spikes) for other methods. Required
spiking concentrations were given and, for laboratory con-
trol standards, required control limits were provided. The
use of laboratory control charts was required. It was also
required that recoveries be compared to control limits,
and that failure to meet control limits would trigger an
investigation to determine the cause of the deviation and
a correction of the problem. The purpose of the internal
quality assurance program was to provide tools for use in
the day-to-day quality assurance program, and tools to be
used in the retrospective review of the data by EPA for
validation and estimation of precision and accuracy. Lim-
ited precision and accuracy goals were stated in terms of
the control limits that were provided for some of the in-
ternal quality control samples.
5. Directives on field replicates (which were to be used to
determine interlaboratory precision) and field blanks.
6. All analytical subcontractors who analyzed water samples
were required to address points 1 through 5 exactly as
described. However, it must be recognized that because of
different capabilities of different methods for different
analytes, not all types of quality assurance samples were
applicable to all methods and analytes.
To reiterate, it was the responsibility of the GCA Corpora-
tion to oversee this quality assurance program on a day-to-day
basis. It was impossible for EPA to manage this function because
more than 6,000 field samples were collected in less than 3
months, and the vast majority of analytical data was not received
by EPA until after nearly all the samples had been collected and
analyzed.
222
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It was the responsibility of EPA to validate the Love Canal
data, and to estimate the precision and accuracy of the validated
data. The process of data validation involved the rejection of
certain analytical results whenever there was compelling evidence
present concerning systematic errors in sampling, preservation,
or analysis associated with those results. These functions were
accomplished by a retrospective (and intentionally redundant) re-
view of all the quality assurance data collected during the proj-
ect. The remainder of this Appendix summarizes the water analy-
ses quality assurance program including the specific actions
taken as a result of the day-to-day quality assurance program,
the data validation process, and the estimation of precision and
accuracy.
METHODS SELECTED FOR ANALYSIS OF WATER SAMPLES
Analytical methods for water analyses were selected with the
recognition that some trade-offs would be necessary between the
desire to acquire the most accurate, precise, and sensitive mea-
surements possible at the current state-of-the-art, and the need
to control costs and find a suitable number of subcontractors
with the experience and capacity to do the analyses. (See Sec-
tion 3.3 for details). Therefore, the following methods were
selected as the ones that best met the project needs.
For the C -C halogenated hydrocarbons and some substituted
benzenes, the method selected was EPA's proposed Method 624 as
described in the Federal Register, Vol. 44, No. 233, December 3,
1979, p. 69532. Briefly, in this method the analytes are purged
from a water sample with a stream of finely divided bubbles of an
inert gas, trapped on the sorbent TENAX, thermally desorbed into
a packed gas chromatographic column, and detected with a mass
spectrometer repetitively scanning from 33 to 260 atomic mass
units (amu) at approximately 5-second intervals.
This method was selected because its scope and limitations
have been studied, and a number of laboratories had extensive ex-
perience with its application to industrial wastewater and drink-
ing water samples. However, the method has not been formally
validated in a multilaboratory study, and the same class of com-
pounds may be measured with other methods which would likely give
somewhat different results for some analytes. The standard re-
porting units for Method 624 are micrograms per liter; further
information about the method is contained in later parts of this
section. Single laboratory precision data for this method was
published in the Journal of Chromatographic Science, 1981, 19,
377.
For most of the other organic compounds on the Love Canal
water monitoring list, the method selected was EPA proposed Meth-
od 625 as described in the Federal Register, Vol. 44, No. 233,
223
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December 3, 1979, p. 69540. Briefly, this method partitions ana-
lytes in a water sample between the pH adjusted water and an or-
ganic solvent, methylene chloride, by mixing the two liquid
phases in a separatory funnel or a continuous extractor. After
separate partitions were formed at pH 12 and pH 2 (in that or-
der), the individual methylene chloride solutions were either
analyzed separately (referred to as Method 625BW) or combined
(referred to as Method 625CW) and analyzed. In either case, the
organic solvent was dried, concentrated to a low volume, and an
aliquot injected into a fused silica capillary gas chromatography
column. Mass spectrometric detection used repetitive scanning
from 35 to 450 amu at approximately 1- to 2-second intervals.
Again, this method was selected because its scope and limitations
have been studied, and a number of laboratories had extensive ex-
perience with its application to industrial wastewater samples.
The application of the fused silica capillary column was an
exercise of an option in a version of Method 625 that was pre-
pared for final rulemaking. Fewer laboratories had experience
with these columns, but they were considered essential because of
the potentially complex mixtures of organic compounds that could
have been present in some Love Canal samples. Method 625 has not
been formally validated in a multilaboratory study, and the same
class of compounds may be measured with other methods which would
likely give somewhat different results for some analytes. The
standard reporting units for Method 625 are micrograms per liter;
further information about this method is contained in later parts
of this section.
The great strength of Methods 624 and 625 is that each method
provides the complete 70 electron volt (eV) mass spectrum for
each analyte. This, together with the retention index, allows a
very high degree of qualitative accuracy, that is, these methods
are highly reliable in the identification of the method analytes
plus any other analytes that are susceptible to the sample prepa-
ration and chromatographic conditions. Another great strength
common to these methods is their utility with numerous analytes
(1 to 100 or more) simultaneously present in a water sample.
Thus, the methods are very cost effective. The weakness of both
methods is that they are not the most precise or sensitive mass
spectrometric methods that could be chosen. Methods that use se-
lective ion monitoring, like that used for 2,3,7,8-tetrachloro-
dibenzo-p-dioxin, are both more precise and sensitive, but are
also much more costly and time consuming to apply when a large
number of analytes are to be measured. The application of fused
silica capillary columns with Method 625 may be considered both a
strength and a weakness. The strength is the high resolution
chromatographic performance of the columns, and the weakness is
that the columns are so new that only a small number of laborato-
ries had experience in using them. Also, their aveiilability was
limited at the time of the study. Additional information on the
scope and limitations of Methods 624 and 625 is presented later
in the section titled "Qualitative Analyses."
224
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A few of the chlorinated hydrocarbon pesticides were known to
be sensitive to the pH 12 extraction conditions of Method 625,
and measurements were desired for certain very toxic pesticides
at levels below the detection limits for Method 625. (See the
general discussion later concerning detection limits). There-
fore, the chlorinated hydrocarbon pesticides and a few related
compounds (PCBs), were measured using EPA proposed Method 608 as
described in the Federal Register, Vol. 44, No. 233, December 3,
1979, p. 69501. Briefly, in this method the liquid-liquid parti-
tion with methylene chloride is carried out with the aqueous
phase at pH 5-9. After separation, drying, and concentration of
the organic solvent to a low volume, an extract aliquot was in-
jected into a packed gas chromatographic column with an electron
capture detector (GC/ECD). The scope and limitations of this
method are well known, and many laboratories have extensive ex-
perience in using it with a wide variety of water sample types.
It was also required that any pesticides identified by this meth-
od be confirmed by the analysis of the same extract with GC/MS
using Method 625 conditions. Method 608 has undergone formal
multilaboratory validation, and a report will be issued in the
near future by EPA. The standard reporting units are micrograms
per liter, and further information about this method is contained
in later parts of this section.
Fluoride was analyzed by either Method 340.1, (Colorimetric,
SPADNS with Bellock Distillation) or Method 340.2 (Potentiomet-
ric, Ion Selective Electrode). These methods appear in Methods
for Chemical Analysis of Water and Wastes, EPA-600/4-79-02T) arid
are approved for National Pollutant Discharge Elimination System
(NPDES) and Safe Drinking Water Act (SDWA) monitoring. Data from
these methods are judged to be equivalent. Method 340.1 involves
distillation to remove interferences, then the sample is treated
with the SPADNS reagent. The loss of color resulting from the
reaction of fluoride with the zirconyl-SPADNS dye is a function
of the fluoride concentration. In Method 340.2, the fluoride is
determined potentiometrically using a fluoride electrode in con-
junction with a standard single junction sleeve-type reference
electrode and a pH meter having an expanded millivolt scale or a
.selective ion meter having a direct concentration scale for fluo-
ride.
Nitrate was analyzed by either Method 353.2 (Colorimetric,
Automated, Cadmium Reduction) or Method 353.3 (Spectrophotomet-
ric, Cadmium Reduction). These methods appear in Methods for
Chemical Analysis of Water and Wastes, EPA-600/4-79-020, and are
approved for NPDES and SDWA monitoring. The methods are chemical-
ly identical, the difference being that Method 353.2 is performed
using automated instrumentation. In these methods, a filtered
sample is passed through a column containing granulated copper-
cadmium (Cu-Cd) to reduce nitrate to nitrite. The nitrite (that
which was originally present plus reduced nitrate) is determined
225
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by diazotizing with sulfani.lamide, and coupling with N-(l-
naphthyl)ethylenediamine dihydrochloride, to form a highly col-
ored azo dye that is measured colorimetrically. Separate, rather
than combined, nitrate-nitrite values are readily obtained by
carrying out the procedure first with, and then without, the
Cu-Cd reduction.
Mercury was analyzed by either Method 245.1 (Manual Cold Va-
por Technique) or Method 245.2 (Automated Cold Vapor Technique).
These methods appear in Methods for Chemical Analyses of Water
and Wastes, EPA-600/4-79-020, and are approved for NPDES and SDWA
monitoring. These methods are chemically identical, the dif-
ference being that Method 245.2 is performed using automated in-
strumentation. In these methods, mercury is measured by a flame-
less atomic absorption procedure based on the absorption of ra-
diation at 253.7 nanometers (nm) by mercury vapor. The mercury
is reduced to the elemental state and aerated from solution in a
closed system. The mercury vapor passes through a cell posi-
tioned in the light path of an atomic absorption spectrophotom-
eter. Absorbance (peak height) is measured as a function of
mercury concentration and recorded.
Selenium was analyzed by Method 270.2 (Atomic Absorption,
furnace technique). This method appears in Methods for Chemical
Analysis for Water and Wastes, EPA-600/4-79-020andisapproved
for NPDES and SDWA monitoring. The furnace technique was used in
conjunction with an atomic absorption spectrophotometer. In this
technique, a representative aliquot of sample is placed in the
graphite tube in the furnace, evaporated to dryness, charred, and
atomized. A light beam from a hollow cathode furnace lamp whose
cathode is made of the element to be determined is directed
through the furnace into a monochromator, and onto a detector
that measures the amount of light absorbed. Absorption depends
upon the presence of free unexcited ground state atoms in the
furnace. Because the wavelength of the light beam is character-
istic of only the metal being determined, the light energy ab-
sorbed is a measure of the concentration of that metal in the
sample.
All other metallic elements were analyzed by Method 200.7
(Inductively Coupled Plasma-Atomic Emission Spectrometric Method
for Trace Element Analysis of Water and Wastes). This method was
proposed for NPDES monitoring in the Federal Register, Vol. 44,
No. 233, December 3, 1979. For the Love Canal study, the diges-
tion procedure outlined in paragraph 8.4 of the Federal Register
was used and the sample was concentrated to one-fifth of the ori-
ginal volume. The basis of the method is the measurement of
atomic emission by an optical spectroscopic technique. Samples
are nebulized and the aerosol that is produced is transported to
the plasma torch where excitation occurs. Characteristic atomic-
line emission spectra are produced by a radio frequency induc-
tively coupled plasma (ICP). The spectra are dispersed by a grat-
ing spectrometer and the intensities of the lines are monitored
226
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by photomultiplier tubes. The photocurrents from the photomulti-
plier tubes are processed and controlled by a computer system.
A background correction technique was required to compensate
for variable background contribution to the determination of
trace elements. Background was to be measured adjacent to ana-
lyte lines on samples during analysis. The position selected for
the background intensity measurement, on either or both sides of
the analytical line, was to be determined by the complexity of
the spectrum adjacent to the analyte line. The position used
must be free of spectral interference and reflect the same change
in background intensity as occurs at the analyte wavelength mea-
sured. Background correction was not required in cases of line
broadening where a background correction measurement would actu-
ally degrade the analytical result.
Qualitative Analyses
For those materials named in this report as Method 608 ana-
lytes, Method 624 analytes, Method 625 analytes, metals analytes,
and anions, the analytical laboratories had available known con-
centration calibration standards, and the results were reported
in micrograms per liter. However, with mass spectrometric meth-
ods, compounds not on the analyte list are often detected, and
may be identified by their mass spectra. These compounds are
designated as qualitative identifications, but concentrations
were not measured because appropriate calibration standards were
not available. In general, Methods 624 and 625 will observe any
compound structurally similar to any Method analyte and with a
molecular weight less than 260 and 450, respectively.
SELECTION OF ANALYTICAL SUBCONTRACTORS
Details of the selection process are given in the GCA Corpo-
ration document Love Canal Monitoring Program, GCA QA/QC Summary
Report. Briefly, EPA provided to the prime contractor the names
of a number of laboratories that were known, from past or ongoing
environmental monitoring programs, to have the generally required
capabilities. Technical evaluation criteria were prepared, pro-
posals were solicited, and a prospective bidders conference was
held. The proposals received were reviewed in terms of the eval-
uation criteria, which included immediate availiability to initi-
ate analyses, quality assurance plan, experience with analyses,
and availability of appropriate equipment, personnel, and manage-
ment. Experience with specific analyses and methods was examined
in detail, and capacities for handling samples in a timely manner
and preferences for executing certain methods were considered.
Finally cost proposals were considered, but this was not the com-
pelling factor. One bidder was not selected because the bid was
considered too low to permit the subcontractor to carry out the
analyses with the required minimum quality assurance program.
Because of the urgency of the program and the deadlines imposed
227
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on EPA, no time was available to conduct a preaward inter-labora-
tory study, with actual samples, to refine the selection process.
LIMITS OF DETECTION/QUANTITATION
The American Chemical Society's (ACS) Subcommittee on Envi-
ronmental Analytical Chemistry published guidelines (Analytical
Chemistry, 1980, 52, 2242) for data acquisition and data quality
evaluation in environmental chemistry. Included in these guide-
lines are recommendations on limits of detection and quantita-
tion. A procedure was developed by EMSL-Cincinnati to determine
a method detection limit that is consistent with the ACS guide-
lines (Environmental Science and Technology, 1981, 1426). As
part of the Love Canal quality assurance plan for water analyses,
sufficient data were collected to apply this procedure to a lim-
ited number of analytes.
Analytical laboratories were required to analyze one labora-
tory control standard (LCS) for each set of samples processed in
a group at the same time on the same day. An LCS was defined as
a solution of analytes of "known concentration in reagent water.
Not all method analytes were included in the LCS' s in order to
contain costs, and only some were at" an appropriate concentration
for the procedure. Where data were available and appropriate,
the method detection limits were calculated from subcontractor-
supplied analytical results; these limits are presented in Table
C-l (laboratory abbreviations are explained in Table 4 of the
text). It must be recognized that the results in Table C-l were
computed from measurements made over a period of weeks, rather
than the recommended procedure of making all measurements in a
single day. Therefore, these values include week to week vari-
ability in the method detection limits.
The data in Table C-l, which are specific to Method 624 or
Method 625 and the reagent water matrix, cover the range of 0.5
to 79 micrograms per liter with a mean of approximately 14 micro-
grams per liter. There was considerable variance among the ana-
lytical laboratories in method detection limits for a given
analyte, and the data suggest that some laboratories were not op-
erating consistently at the state-of-the-art possible with the
methods. This is neither unusual nor unexpected.
The data in Table C-l, which were determined in reagent wa-
ter, may be applied reasonably to the sample matrices of the Love
Canal samples. It has been shown that Methods 624 and 625 are
not sensitive to the different matrices of the ground, drinking,
surface, sump, or storm sewer waters of the Love Canal area. (See
the later section on data validation), Similarly, it is reason-
able to assume that the method detection limits of most of the
organic analytes not shown in Table C-l fall into the same range
of 0.5 to 79 micrograms per liter. Again, considerable variance
in detection limits probably existed among the analytical labora-
tories .
228
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TABLE C-l. MEASURED METHOD DETECTION LIMITS IN MICROGRAMS
PER LITER FROM ANALYSES OF LABORATORY CONTROL STANDARDS
Analytical
Analyte
Method 624
Benzene
Chlorobenzene
Chloroform
Bromoform
sym-Tetrachloroe thane
Carbon tetrachloride
Trichloroethylene
Tetrachloroethylene
Toluene
Method 625
1 , 4-Dichlorobenzene
1,2, 4-Trichlorobenzene
1,2,3, 4-Tetrachlorobenzene
2,4, 6-Trichlorophenol
Pentachlorophenol
2 , 6-Dinitrotoluene
4-Nitrophenol
2-Chloronaphthalene
0-BHC
Fluor anthene
Di-n-butylphthalate
ACEE PJBL
26 16
16 17
29 17
42 40
23 31
37 30
26 23
21 28
— —
23
3.5 9.6
17
17
19
16
6.4
1.8 15
9.5
2.4 —
27
GSNO
16
12
8.6
14
8.1
13
9.4
13
—
20
17
—
24
21
25
14
17
—
20
14
Laboratory Code
CMTL TRW EMSL-Cin
11 2.4 4.4
8.3 2.0 6.0
5,5 1.6
1.8 4.7
1.7 6.9
2.7 2.8
1.6 1.9
2.4 4.1
9.5 — 6.0
34 — 5.0
32 — 1.9
0.5
2.7
30 ~ 3.6
1.9
21 — 2.4
1.9
4.2
2.2
79 — 2.5
229
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Table C-2 gives estimated method detection limits generated
from statements in the methods, instrumental detection limits,
precision data, and experience using them. They were not
rigorously determined but are levels expected to be reported by
an analyst using the specified methods. Table C-3 gives measured
method detection limits for Method 608 in reagent water. These
were measured by one of the subcontractor analytical laborato-
ries, and may be considered typical of the other laboratories'
probable performance.
TABLE C-2. ESTIMATED METHOD DETECTION LIMITS
FOR ALL LABORATORIES
Estimated
Detection
Analyte
Arsenic
Antimony
Barium
Beryllium
Cadmium
Chromium
Copper
Lead
Mercury
Nickel
Selenium
Silver
Thallium
Zinc
Fluoride
Nitrate
Limit (fig/liter)
53
32
2
0.3
4
7
6
42
2
15
10
?
40
2
200
100
230
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TABLE C-3. MEASURED METHOD DETECTION LIMITS IN MICROGRAMS PER
LITER FOR METHOD 608 IN REAGENT WATER'
Analyte
ff-BHC
p-BHC
6-BHC
T-BHC
DDD
DDE
DDT
Endosulfan I
Endosulfan II
Endosulfan Sulfate
Heptachlor
Heptachlor Epoxide
Aldrin
Dieldrin
Endrin
Chlordane
Toxaphene
PCB 1242
Limit
.003
.006
.009
.004
.011
.004
.012
.014
.004
.066
.003
,083
.004
.002
.006
.014
.235
.065
'Measured by SWRI under contract to EMSL-Cincinnati
Data from the Love Canal samples include few reports of con-
centrations below the method detection limits in Tables C-l, C-2,
and C-3, but the range of values reported in Table C-l is a
function of the analytical laboratory. Reports of "trace" for
analytes in field samples are the result of subjective judgments
by individual laboratories, and represent detections that were of
231
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sufficient magnitude to identify the substance, that is, above
the limit of detection, but not of sufficient magnitude to mea-
sure the amount present, that is, below the method quantitation
limit. The meaning of "trace" is further obscured by the vari-
ance in method detection limits among laboratories.
Method detection limits were not used to validate data in the
Love Canal data base. Variability in quantitation and detection
limits among laboratories is a well-known phenomenon and is un-
avoidable. Some laboratories may have quantified substances that
others called "trace," or did not report the substances. These
occurrences do not invalidate the results. At the worst, the
method detection limits are at the low micrograms per liter level
(none exceed 200). Because the conclusions of the study were
based on samples contaminated at several orders of magnitude or
higher concentrations, that is, parts per million to parts per
thousands, the observed variability and magnitudes of the method
detection limits had no affect on the overall conclusions of the
study. The method detection limits given in Table C-l that are
below approximately 10 micrograms per liter, and given in Tables
C-2 and C-3, are believed to represent the state-of-the-art with
the methods.
ANALYTICAL LABORATORY PERFORMANCE EVALUATIONS
The Quality Assurance Branch (QAB) of EMSL-Cincinnati con-
ducted extensive performance evaluations (PE) of the analytical
laboratories before and during the course of the analytical work.
The purpose of this effort was to support the day-to-day quality
assurance program of the prime contractor, GCA Corporation. Spe-
cially prepared samples of method analytes and detailed instruc-
tions were sent overnight to the prime contractor's sample bank
at Love Canal, using chain-of-custody procedures. The prime con-
tractor sent these unknown PE samples to the analytical labora-
tories at approximately 1-month intervals, along with shipments
of Love Canal samples. Results from the PE samples were sent di-
rectly to QAB, which judged them as acceptable or nonacceptable,
and reported each evaluation series immediately to the prime con-
tractor 's quality assurance officer.
The prime contractor contacted each subcontractor analytical
laboratory by telephone on receipt of the PE sample results, and
informed the laboratory of the nature of the results. Discus-
sions centered on the unacceptable values and corrective actions
that were required. These results and the required corrective
actions were also discussed during laboratory site visits. Table
C-4 is a summary of the percentages of acceptable PE results by
analytical method analyte group and analytical laboratory. In
order to have an acceptable result, the analytical laboratory
must have correctly identified the analyte and measured its con-
centration to within the acceptance limits established by QAB.
The general performance of the laboratories in identification was
232
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TABLE C-4. PERCENTAGES OF ACCEPTABLE PERFORMANCE EVALUATION RESULTS
Analytical
Method
Group One
Method 624
Method 625
Method 608
Metals Methods
Anions Methods
Group Two
Method 624
Method 625
Method 608
Metals Methods
Anions Methods
Total Organic
Carbon
Group Three
Method 624
Method 625
Method 608
Metals Methods
Anions Methods
Number of
Analytes
12
12
7
14*
2
12
12
7
14
2*
1
12
12
7
14
2*
PJBL GSNO
92 77
100T 54
88 71
93
100
100 92
58
100
93
100
—
100 92
100 47
25 71
93
50
Analytical Laboratory Code
SWRI CMTL ACEE TRW ERGO AES EMSL-Cin
58 54 33
58 46 69 — — — 58
50 88 86 -- — -- 71
93
— 100
58 100 — — — 92
50 55 — — — 64
100 63 — — — 100
— 100 — 80
7 c TC
— — — — —~~ — • — i j — / j
„ .. - - _ o -
100 — 75 92 — — 92
77 — 67 100 — — 92
86 — 100 78 — — 100
86 — 100
— 100 100*
Data obtained with conventional packed column
*Two concentrations of each analyte were included in the PE sample.
'Only one of four results reported
233
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excellent, with very few analytes missed. The unacceptable re-
sults in Table C-4 were due largely to concentrations measure-
ments that were outside the acceptable range. As previously
noted, Method 625 employed the relatively new fused silica capil-
lary columns, and there was some initial difficulty in adjusting
to this in some laboratories. The PE samples served to assist in
this adjustment and to provide data on the applicability of the
columns.
One hundred and fifty sets of quality control (QC) samples
for Methods 624, 625, 608, trace metals, and nitrate/fluoride
were provided to the analytical laboratories to assist their
within-laboratory quality control programs. These samples were
provided with true values which were retained by the prime con-
tractor, and used in a manner similar to the PE samples.
Information from PE and QC samples was not used to estimate
precision and accuracy of the analytical measurements or to vali-
date data for the Love Canal monitoring program, because the PE
and QC samples were concentrates in an organic solvent that were
added to reagent water at the analytical laboratory before the
application of the method. Therefore, although the analytical
laboratories were unaware of the true concentrations, they were
aware that the samples were PE and QC samples and may have taken
unusual care in their analyses. The purpose of the PE and QC
samples was to discover problems with the execution of the meth-
ods and enable corrective action by the prime contractor on a
timely basis.
SAMPLE PRESERVATION
Directions for sample preservation were included in the
analytical methods referenced previously. For the organic com-
pound methods {624, 625, and 608), preservation requirements in-
cluded shipment and storage of samples in iced or refrigerated
containers. There was a very high degree of compliance with
these preservation requirements.
Maximum holding times for samples before analyses were also
specified in the methods. There was a high percentage of samples
that were not analyzed within the specified holding times because
the magnitude of the analytical requirements of the Love Canal
study, plus numerous other on-going environmental studies, liter-
ally overwhelmed the national capacity for low-level chemical
analyses. The situation was especially severe with regard to the
organics analyses using Methods 624 and 625, which employ state-
of-the-art gas chromatography/mass spectrometry technology, and
Method 608. An analysis of the sample holding times revealed
that most Method 608 and Method 625 samples were extracted within
the 7-day holding time, and analyzed within the 30-day extract
holding time. However, most Method 624 samples were held longer
than the 14-day holding time.
234
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A study was undertaken by EMSL-Cincinnati to determine the
effects of prolonged sample holding times on the stability of
Method 624 analytes. Representative compounds that were known to
be susceptible to biological degradation in nonchlorinated water
at submicrogram per liter concentrations were added to a non-
chlorinated well water sample and a nonchlorinated surface (lake)
water sample at concentrations of 100 micrograms per liter. The
samples were stored at 6° C in standard sample containers for up
to 50 days, the longest period that any Love Canal Method 624
sample was held. Multiple analyses according to Method 624
showed that at this concentration, which was representative of
the concentrations found in many Love Canal samples, there were
no detectable losses of any of the study compounds over the 50-
day period.
An extensive analysis was made of the holding times on all
Method 624 samples to seek a correlation between actual holding
time and the presence or absence of compounds known to be sus-
ceptible to losses at the submicrogram per liter level. The con-
centration range of concern was generally from 5 to 3,300 micro-
grams per liter. No correlation was found and it was concluded
that the extended holding times for Method 624 samples did not
impact the reliability of the data for the compounds susceptible
to losses at submicrogram per liter levels. No samples were
invalidated because holding times were exceeded.
DATA VALIDATION PROCEDURE
Validation of data is the systematic process of rejecting
analytical results whenever compelling evidence exists of sys-
tematic errors in sampling, preservation, or analysis associated
with those results. Data validation for all methods was based on
the retrospective statistical analysis of results from a series
of quality assurance samples that were analyzed by all laborato-
ries. The form of the quality assurance was slightly different
depending on the method, but a common feature was the analysis by
EMSL-Cincinnati of approximately 5 percent of the water samples.
Each of the samples analyzed by EMSL-Cincinnati was a member of a
group of three that were collected at Love Canal at the same time
and place by the sampling team. Two of these samples were de-
livered to the same subcontractor laboratory with different sam-
ple numbers and, therefore, were blind duplicates. The third,
with a different sample number, was delivered to EMSL-Cincinnati.
The details of the validation process are given in this section.
The section entitled "Estimates of Data Precision" contains addi-
tional information obtained from the field triplicate samples.
Methods 624 and 625
For Methods 624 and 625, the principal validation tool was a
series of quality control compounds, often called surrogate ana-
lytes, that were added to each water sample. The compounds se-
lected as surrogates were valid method analytes that were neither
235
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commercially produced nor naturally occurring. Therefore, it was
highly unlikely that any of them would be found in any environ-
mental sample. The compounds fluorobenzene and 4-foromofluoroben-
zene were added by the analytical laboratories to each water sam-
ple intended for Method 624 at a concentration in the range of 5
to 25 micrograms per liter. The compounds 2-fluorophenol, 1-
fluoronaphthalene, and 4,4'-dibromooctafluorobiphenyl were added
by the analytical laboratories to each water sample intended for
Method 625 at a concentration in the range of 5 "to 25 micrograms
per liter. Analytical laboratories reported the quantities added
(true values) and the amounts measured. Statistics were computed
by EMSL-Cincinnati in terms of the percentage recoveries of the
amounts added to allow comparisons among laboratories that added
different amounts within the specified range.
The recoveries (percentages of the true values) for the five
surrogates in both methods by all analytical laboratories were
analyzed statistically to determine if there were any significant
differences related to the types of samples, that is, ground wa-
ter, drinking water, surface water, sump water, or storm sewer
water. No statistically significant differences were found, that
is, there were no unusual matrix effects in any of these sample
source types, and all subsequent data analyses were conducted by
combining results from different sample types. The recoveries for
each surrogate were tested for normality using several standard
statistical tests. The conclusion was that the data were approx-
imately normally distributed, and that use of standard deviations
and statistical tests based on normal theory were justified.
The standard for performance with the surrogate analytes was
established with the 5 percent of the water samples analyzed by
EMSL-Cincinnati, which developed Methods 624 and 625 and operated
in control based on extensive experience. Table C-5 contains a
summary of the statistics and the lower control limits that were
expressed as 99 percent confidence limits. No upper control lim-
its were used because there were very few reports of excessively
high recoveries. High measurements are indicative of positive
interferences that were precluded by the nature of the surrogates
and the high selectivity of the mass spectrometric detector. Low
percentages of true values are indicative of losses due to care-
less handling, reduced equipment efficiency, or inadequate sensi-
tivity. Lower control limits were set at the 99 percent confi-
dence level to ensure the high probability that any recoveries
below them were due to nonrandom systematic method errors.
It should be pointed out that the lower acceptance limits
(Table C-5) for the three Method 625 surrogates 2-fluorophenol,
1-fluoronaphthalene, and 4,4'-dibromooctafluorobiphenyl were not
the same as the lower control limits provided initially to the
analytical subcontractors for use in their internal quality con-
trol programs. The lower internal quality control limits that
236
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were provided to the analytical subcontractors (Quality Assurance
Plan, Love Canal Study, LC-1-619-206) were based on data obtained
fromMethod625using a packed gas chromatography column. As
noted previously in the section entitled "Methods Selected for
the Analysis of Water Samples," fused silica capillary column
technology was selected for use with Method 625. It was recog-
nized that while significant advantages were to be gained through
the selection of this relatively new column technology, no data
on precision would be available prior to the study. Therefore,
packed column control limits were provided as guidelines for use
by the analytical subcontractor laboratories.
As part of the retrospective data validation process, accep-
tance limits were developed based on the actual experience de-
rived from the fused silica capillary columns. These limits,
which are reported in Table C-5, are somewhat lower than the
packed column control limits and reflect relatively greater vari-
ability in measurements obtained from the capillary columns.
The relatively greater variability in capillary column measure-
ments was judged acceptable in light of the considerable advan-
tages derived from the new technology. In addition, it should be
pointed out that even though somewhat greater variability was
obtained from the fused silica capillary column technology, the
data validation confidence limits were not altered. That is, the
original packed column control limits and the derived capillary
column acceptance limits were both set at the 99 percent confi-
dence level.
In order to invalidate the data from a sample, it was re-
quired that at least two surrogate compounds in the sample have
their recoveries out of control. Out of control low recoveries
of two surrogate compounds is strongly suggestive of poor method
execution, and the high probability that all other method ana-
lytes would be measured low or completely missed because of poor
method execution.
With Method 624, data from five Love Canal samples were in-
validated. One of these was a field blank, three were sump sam-
ples, and one was a ground-water sample. Three subcontractor
laboratories were represented, and no analytes were reported in
any of these samples except the laboratory contaminant methylene
chloride and some trace levels of other analytes. (See the next
section). With Method 625, data from 12 samples were invalidated
because at least 2 of the 3 surrogate recoveries were below the
lower control limits shown in Table C-5. The invalidated data
did not include any significant analyte measurements, but includ-
ed several traces and large quantities of the phthalate ester
laboratory contaminants. The invalidated Method 625 data were
mainly from sump, ground water, or field blank samples and in-
cluded measurements from four laboratories.
237
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TABLE C-5. SUMMARY STATISTICS AND LOWER CONTROL LIMITS FOR
METHODS 624 AND 625 SURROGATES FROM EMSL-CINCINNATI MEASUREMENTS
Relative
Number Mean Standard Lower Con-
Surrogate of Recovery Deviation trol Limit
Analyte Samples (Percent) S.D. (Percent) (Percent)
Fluorobenzene 22
4-Bromofluoro-
benzene 22
2-Fluorophenol 26
1-Fluoronaphtha-
lene 26
4,4'-Dibromoocta-
fluorobiphenyl 26
99
99
57
73
79
10
13
20
23
24
10
13
36
32
30
68
60
1
2.8
8.3
S.D.j Standard deviation
Invalid Ground-Water Samples
There were 28 ground-water Method 624 samples from bedrock B
Wells that were contaminated only by chloroform. It is well es-
tablished that this compound is formed during the disinfection of
water with chlorine to prepare water suitable for human consump-
tion. It was determined by the EPA Environmental Research Labo-
ratory in Ada, Oklahoma, which was responsible for the ground-
water monitoring program, that the wells from which these samples
were taken were not purged adequately prior to sampling. Ordi-
nary hydrant water (drinking water) was used as a drilling fluid
during the bedrock well drilling process, and type B Wells were
supposed to have been purged of these fluids before sampling.
Consequently, all samples from these wells were invalidated, not
because the analyses were at fault, but because the samples may
not have been representative of the ground water. While a few
other ground-water samples also contained chloroform, other con-
taminants were present; therefore, samples from these wells were
not invalidated.
Laboratory Contamination
Methylene chloride was the solvent used in Method 625, and it
was an analyte in Method 624. There were 84 water samples analy-
zed by Method 624 in which methylene chloride was the only re-
ported analyte, and 94 percent of these reports came from 2 lab-
oratories, CMTL and GSNO. This evidence strongly suggested the
presence of laboratory contamination that was not unexpected with
such highly sensitive analytical methodology. Therefore, although
238
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a few reports of methylene chloride may have been valid, the
overwhelming number were very likely laboratory contaminants, and
it was impossible to distinguish the former from the latter. Con-
sequently, all reports of methylene chloride in water samples
were deleted from the validated data.
Late in the data reporting period, after the methylene chlo-
ride problem was discovered, one of the laboratories was inspec-
ted by EPA personnel.- A large opening was found in the labora-
tory between the area where the methylene chloride extractions
were conducted and the room where the analytical instrumentation
was located. This finding supported the strong probability that
methylene chloride was a laboratory contaminant in at least one
of the laboratories.
There were a very large number of reports for two compounds,
bis(2-ethylhexyl)phthalate and dibutyl phthalate, in both real
and quality control samples. There also were significant differ-
ences in the amounts of these compounds reported in several labo-
ratory duplicates. Finally, it is well-known that these com-
pounds are widely used plasticizers and are frequently used in
bottle cap liners. Many of the early samples that arrived at
EMSL-Cincinnati for analysis had poorly fitted and leaking Teflon
cap liners. This was corrected later in the study and fewer of
these phthalates were observed. On this basis, all reports of
these two compounds in samples were judged highly unreliable and
all reports were removed from the validated data.
Method 608
Validation of data from samples analyzed by Method 608 was
based on the quality control requirement that an LCS was to be
analyzed with each batch of samples processed in a group at the
same time. Recoveries of LCS analytes were evaluated, and if un-
acceptable recoveries were reported, all of the data obtained
with Method 608 on that day by that laboratory were invalidated.
Using this approach, all the data obtained by one laboratory on
one day were invalidated because the laboratory reported zero LCS
recoveries, suggesting major method execution errors or instru-
ment failures.
Method 608 employs an electron capture gas chromatographic
detector, and is subject to false positive identifications. In
order to minimize these errors, two column confirmation and gas
chromatography/mass spectrometry (GC/MS) confirmations were re-
quired for all Method 608 results. However, GC/MS confirmation
was limited by the difference in detection limits between the
methods. Users of the Love Canal data should be aware of the
probability that low level, less than 0.5 micrograms per liter,
measurements by Method 608 were not confirmed by GC/MS.
239
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Metals and Anions
Validation of data from samples analyzed for metals and the
anions fluoride and nitrate was based on the quality control re-
quirement that a certain percentage of samples were spiked with
the analytes at a specified concentration. Specifically, the
first 10 samples from each type of water sample (ground, sump,
drinking, storm sewer, and surface), and 5 percent of the remain-
ing samples, were spiked with these analytes at concentrations in
the range of 10 to 10,000 micrograms per liter. The concentra-
tions were selected as appropriate for the analyte, and the lab-
oratories were required to measure the background levels first
and subtract these from the spike concentrations before the per-
centage recoveries were computed.
The standard of performance with these methods was estab-
lished by the results obtained from EMSL-Cincinnati measurements
of 5 percent of the samples. The EMSL-Cincinnati recoveries for
the 14 metal and 2 anion parameters were tabulated by parameter
and sample source type. The mean recovery and standard deviation
were calculated for the total population and for each sample
type. A mean recovery of +11 percent of the actual spike value
(based on the total population) was used as the criterion for
valid data.
The spike recovery data from the other analytical laborator-
ies were compared with the criterion, and data meeting it were
accepted as valid. For some data, poor spike recoveries could be
traced to improper spiking technique, and the data were ruled
valid. In other cases, no explanation could be found for the
poor recoveries and all data analyzed on that day, in that sample
source type, by that laboratory, were ruled invalid. Overall,
some data from two laboratories were invalidated, and in every
case these were all measurements of one metal in a particular
source type on a particular day.
ESTIMATES OF DATA PRECISION
The purpose of the field triplicate samples described at the
beginning of the data validation section was to establish inter-
laboratory and intralaboratory precision. In addition, some
methods required taking two aliquots of 10 percent of the samples
to obtain further information about intralaboratory precision.
However, a high percentage of the total samples gave all analytes
below detection limits, and insufficient information was avail-
able to estimate the precision of the measurements from these
samples.
With Method 625, close to 75 percent of all water samples
contained no analytes above the method quantitation limit. An
additional 10 percent of the water samples contained only trace
240
-------
quantities. These findings were reflected in the results ob-
tained with the field triplicate samples and laboratory dupli-
cates, and insufficient results were available from these samples
to estimate precision. Similar observations were made with all
other methods.
Data precision may be estimated using the results of the
measurements of the laboratory control standards that were de-
scribed earlier under Limits of Detection/Quantitation. This is
a less desirable approach because the LCS measurements do not in-
clude the variability associated with sampling, transportation,
storage, and preservation of samples. Also, these data may have
been obtained over a period of weeks by some laboratories, and
the values may include wee"k-to-week variations that may signifi-
cantly exceed variations within a given analysis day. Neverthe-
less, lacking the information from the replicate field samples,
the LCS measurements may be used to provide rough estimates of
data precision.
Table C-6 shows the relative standard deviations for repli-
cate measurements of Method 624 and Method 625 analytes in LCS
samples. No statistics were computed unless at least five repli-
cate measurements were available. Some laboratories did not ana-
lyze a sufficient number of some types of samples to accumulate
five LCS measurements. All the LCS concentrations were in the
range of 10 to 50 micrograms per liter. The precision of any
single measurement of a Method 624 or Method 625 analyte in any
Love Canal water sample, at the 95 percent confidence level, may
be estimated using the formula:
Analytical Result + 2 x (RSD from Table C-6).
The RSD should be selected from Table C-6 according to the ana-
lyte measured and the laboratory analyzing the sample. If the
exact analyte is not in Table C-6, a structurally similar analyte
may be used? for example, if the analyte of interest is 2-nitro-
phenol, the RSD for 4-nitrophenol may be used. If RSD data for
the reporting laboratory is not in Table C-6, use the mean RSD of
all laboratories reporting that analyte. Additional single lab-
oratory precision data for Method 624 was published in J. Chroma-
tographic Science, 1981, 377. For metals and anions, a similar
estimate may be made using the relative standard deviations pre-
sented in Table C-7.
Precision estimates were not used to validate the Love Canal
data. Data validation procedures are explained in detail in the
previous section entitled, "Data Validation Procedures."
ESTIMATES OF DATA ACCURACY
Method 624 is well established as a method without bias when
it is used to analyze samples that have a matrix similar to the
241
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TABLE O6. RELATIVE STANDARD DEVIATIONS (RSD) FOR ORGANIC
ANALYTES IN LABORATORY CONTROL STANDARDS
Analytical Laboratory Code
Analyte ACEE PJBL GSNO CMTL TRW
Method 624
Benzene 42
Chlorobenzene 28
Chloroform 55
Broraoform 77
sym-Tetrachloroethane 38
Carbon tetraehloride 53
Trichloroethylene 44
Tetrachloroethylene 36
Toluene —
Method 625
1 » 4~Dichlorobenzene
1 , 2 , 4-Tr ichlorobenzene
1 , 2 , 3 , 4-Tetrachlorobenzene —
2, 4,6-Trichlorophenol —
Pentachlorophenol —
2, 6-Dinitrotoluene —
4-Nitrophenol —
2-Chloronaphthalene —
0-BHC
Fluoranthene
Di-n-butylphthalate —
^As reported in J. Chroma tographic
11
12
12
39
31
17
18
23
—
37
30
32
47
52
45
40
32
30
—
38
Science,
27 12 4.3
25 9.4 3.9
16 — 5.3
42 — - 2.6
29 — 2.7
33 -- 14
19 — 5.6
30 — 7.6
__ Ti _„
79 32
62 32
— —
63
59 87
70
— 109
56
—
55
73 77
1981, 377; all
EMSL-Cinf
7
10
3
7
12
4
2
6
9
17
15
_
20
25
16
42
12
7
21
17
data
.4
.6
.5
.9
.7
.3
_
.7
obtained during a single work shift
242
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TABLE C-7. RELATIVE STANDARD DEVIATIONS (RSD) FOR INORGANIC
ANALYTES IN WATER SAMPLES
Analytical Laboratory Code
Analyte
Arsenic
Antimony
Barium
Beryllium
Cadmium
Chromium
Copper
Lead
Mercury
Nickel
Selenium
Silver
Thallium
Zinc
Fluoride
Nitrate
ERGO
8.1
12
5.9
5.7
13
11
17
13
19
12
13
12
16
20
10
82
PJBL
33
38
46
12
14
14
12
11
25
10
23
39
38
11
10
15
SWRI
11
36
21
29
25
38
32
31
25
30
47
46
15
22
6
11
EMSL-Cin
11
43
4.
7.
5.
8.
5.
16
10
30
8.
3
15
19
13
2.
3
3
6
1
3
7
6
reagent water matrix used to calibrate the procedure. The sample
types analyzed in this study had no unusual matrix effects, and
the Method 624 results are without bias. (See the discussion of
surrogate recoveries as a function of water sample type in the
Data Validation Procedures section).
Data from Methods 625 and 608 have a significant bias because
the liquid-liquid partition is not 100 percent efficient, and
243
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these methods do not provide a procedure to correct for these
losses. Recoveries of Method 625 and 608 analytes generally fall
in the 50 to 90 percent range (Table C-5), and this was confirmed
in this study by measurements of a number of analytes in labora-
tory control standards.
Measurements of metals and the two anions were without sig-
nificant bias in the Love Canal samples. This was discussed pre-
viously in the section on data validation.
Estimates of data accuracy were used to validate the Love
Canal data. These procedures for surrogate analytes and other
analytes were described in detail in the "Data Validation Proce-
dures" section.
SUMMARY OF MAJOR ACTIONS TAKEN AS A RESULT OF THE GCA CORPORA-
TION'S QUALITY ASSURANCE FUNCTION
The activities of the prime contractor in the day-to-day
quality assurance program are described in detail in the Love
Canal Monitoring Prog rain, GCA QA/QCSummary Report on the Love
Canal study. The purpose of this section is to summarize briefly
the major QA actions initiated by the GCA Corporation.
The prime contractor routinely discussed, by telephone and
during site visits, the results of the external quality assurance
samples with the analytical laboratories. Requirements for cor-
rective action were provided during these discussions. The prime
contractor also monitored the results from the internal quality
assurance program, and discussed these with the analytical labo-
ratories during telephone conversations and site visits. Again,
requirements for corrective action were provided.
One significant action that resulted from the day-to-day
quality assurance program was the removal of the laboratory PJBL
from the analysis of samples by Method 625 in water, soils, and
sediment. During a site visit and during discussions of the in-
ternal and external quality assurance samples, it was discovered
that PJBL was using packed columns with Method 625, and did not
have the capability to analyze the samples with the fused silica
capillary columns.
All previous results using Method 625 provided by PJBL were
therefore invalidated, work on Method 625 was suspended at PJBL,
and TRWW replaced PJBL for the analysis of Method 625. Eventu-
ally, PJBL developed the capability to use the fused silica
capillary columns and all the sample extracts were reanalyzed.
Details of this incident and other activities of the prime
contractor are given in the Love Canal MonitoringProgram, GCA
QA/QC Summary Report referenced earlier.
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APPENDIX D
QUALITY ASSURANCE FOR SOIL, SEDIMENT, AND BIOTA SAMPLES
OVERVIEW OF QUALITY ASSURANCE PROGRAM
This Appendix summarizes the quality assurance activities and
data validation procedures used in the soil, sediment, and biota
analyses. Details of the quality assurance plans are presented
in a four-part document entitled Quality Assurance Plan, Love
Canal Study, LC-1-619^206, that was issued by the GCA Corpora-
tion, the prime contractor for the project, and approved by the
EPA quality assurance officers. As was mentioned previously,
that document consists of a main volume plus Appendix A on sam-
pling procedures, Appendix B on analytical procedures, and Ap-
pendix Q on the subcontractor's QA plans. A more detailed dis-
cussion of the results of the prime contractor's and subcontrac-
tor's quality assurance efforts is contained in the Love Canal
Monitoring Program,GCA QA/QC SummaryReport prepared by the GCA
Corporation.Thesedocuments(availablefrom NTIS) should be
consulted for more details on the project.
The design of the soil, sediment, and biota monitoring pro-
gram at Love Canal and the related quality assurance plans were
developed by EPA and described in detail to the prime contractor.
This guidance was intended to establish minimum standards for
quality assurance, and it was expected that the GCA Corporation
and subcontractors would amplify the requirements in their plans.
During the design, study, and data evaluation phases of the Love
Canal project, the plans and results were reviewed by an inde-
pendent group, the sampling protocols study group of the EPA's
Science Advisory Board.
It was the responsibility of the prime contractor to oversee
the day-to-day quality assurance programs of the subcontractors
using the guidance provided by EPA and the approved plans. This
guidance formed the basis for the GCA Corporation quality assur-
ance plan document that was mentioned earlier. Briefly, the soil,,
sediment, and biota quality assurance guidance provided by EPA
included the following items.
245
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1. Directives on sample collection
2. Directives on analytical methods
3. Directives on the external quality assurance program, in-
cluding the use of performance evaluation samples and
quality control samples provided by EMSL-Cincinnati. The
purpose of the external quality assurance program was to
give the prime contractor some of the tools necessary to
oversee the day-to-day quality assurance program.
4. Directives on the internal quality assurance program in-
cluding required measurements of gas chromatography/mass
spectrometry (GC/MS) reference compounds, method blanks,
laboratory control standards, laboratory duplicates, sur-
rogate analytes for modified Methods 624 and 625, and
known additions (spikes) for other methods. Required
spiking concentrations were given. The purpose of the in-
ternal quality assurance program was to provide tools for
use in the day-to-day quality assurance program, and tools
to be used in the retrospective review of the data by EPA
for validation and estimation of precision and accuracy.
5. Directives on field replicates, which were to be used to
determine interlaboratory precision, and field blanks
6. All analytical subcontractors who analyzed soil, sediment,
and biota samples were required to address points 1
through 5 exactly as described. However, it must be rec-
ognized that because of different capabilities of differ-
ent methods for different analytes, not all types of qual-
ity assurance samples were applicable to all methods and
analytes.
To "reiterate, it was the responsibility of the GCA Corpora-
tion to oversee this quality assurance program on a day-to-day
basis. It was impossible for EPA to manage this function because
over 6,000 field samples were collected in less than 3 months,
and the vast majority of analytical data was not received by EPA
until nearly all the samples were collected and analyzed.
It was the responsibility of EPA to validate data for the
Love Canal data base and to estimate the precision and accuracy
of the validated data. Validation involved the rejection of cer-
tain analytical results whenever there was compelling evidence of
systematic errors in sampling, preservation, or analysis asso-
ciated with those results. These functions were accomplished by
a retrospective (and intentionally redundant) review of all the
quality assurance data collected during the project. The balance
of this Appendix summarizes the quality assurance program in-
cluding the specific actions taken as a result of the day-to-day
quality assurance program, the data validation process, and the
estimation of precision and accuracy.
246
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METHODS SELECTED FOR ANALYSIS OF SOIL AND SEDIMENT SAMPLES
Analytical methods for soil and sediment analyses were se-
lected with the recognition that some trade-offs would be neces-
sary between the desire to acquire the most accurate, precise,
and sensitive measurements possible at the current state-of-the-
art, and the need to control costs and find a suitable number of
subcontractors with the experience and capabilities to do the
analyses. Some of these trade-offs were discussed in Section 3.3
of the report, with emphasis on the pre-study goals for accuracy,
precision, and limits of detection/quantitation. The following
methods were selected as the ones that best met the project
needs.
For the C,-CU halogenated hydrocarbons and some substituted
benzenes, the method selected was a modification of EPA's pro-
posed Method 624 as described in the Federal Register, Vol. 44,
No. 233, December 3, 1979, p. 69532, and presented in Appendix C,
Quality Assurance for Water Samples. The modifications to Method
624 for soil and sediment analyses consisted of placing a mixture
of soil or sediment and reagent water in a modified screw-top
vial and purging as in Method 624, except that the sample-water
mixture was heated to 55°C during the purge. The rationale for
this modification was that the method analytes are not sorbed
strongly on the soil/sediment particulate matter, because their
structures do not generally contain polar functional groups, and
the analytes have typically low solubilities in water and rela-
tively high vapor pressures at ambient temperatures. Therefore,
at 55°C and with the agitation of the purge gas, the method ana-
lytes would rapidly equilibrate between the sorbed and liquid
phases, and be subject to purging from the water as in Method
624.
The modified soil and sediment Method 624, which is desig-
nated Method 624PS in the Love Canal data base, has not been for-
mally validated in a multilaboratory study. Only unpublished in-
ternal EPA reports describe the method and preliminary results.
This same class of compounds may be measured with other methods
which would likely give somewhat different results for some
analytes. Method 624PS is not limited to the analytes listed in
Method 624 (as amended for the Love Canal study), but will ob-
serve any compound structurally similar to the method analytes
and with similar physical and chemical properties. The method is
limited to compounds with a molecular weight from 33 to 260
atomic mass units (amu), because this was the limit of the mass
spectrometer scan. The standard reporting units for Method 624PS
are micrograms per kilogram, and further information about the
method is contained in later parts of this section.
For most of the other organic compounds on the Love Canal
monitoring list, the method selected was a modification of EPA's
proposed Method 625 as described in the Federal Register, Vol.
247
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44, No. 233, December 3, 1979, p. 69540, and presented in Ap-
pendix C, Quality Assurance for Water Samples. The modifications
to Method 625 for soil and sediment analyses consisted of ex-
tracting the pH adjusted soil or sediment with methylene chloride
using a high speed mechanical stirrer. Separate extractions at
pH 12 and pH 2 (in that order) were followed by centrifuging to
facilitate phase separation. The separated individual methylene
chloride solutions were dried, concentrated to a low volume, and
either analyzed separately (Method 625BS in the Love Canal data
base) or combined and analyzed (Method 625CS in the Love Canal
data base). The optional Method 625 fused silica capillary gas
chromatography column was used with modified Method 625. In
addition, an optional gel permeation chromatographic procedure
was included in the method for preprocessing heavily contaminated
samples before gas chromatography, but it was determined early in
the study that preprocessing was not necessary for all samples.
Only two analytical laboratories, GSRI and SWRI, received heavily
contaminated soil/sediment samples in the early part of the study
and became accustomed to routine application of the gel permea-
tion chromatographic procedure.
The principal modifications to Method 625 for soil and sedi-
ment analyses were the use of a high speed mechanical stirrer,
centrifuging to separate phases, and the optional gel permeation
chromatography. These modifications to Method 625, originally
established to allow the application of Method 625 to sludges
formed in wastewater treatment plants, were developed previously
by the Midwest Research Institute (MWRI) under contract to EPA.
A final report on this project has been prepared, peer reviewed,
and is scheduled for release during 1982. This report, and other
internal EPA studies, indicated that the modifications were suc-
cessful, and the method was a viable choice. In particular, the
MWRI report indicated good recoveries from the gel permeation
chromatographic preprocessing, which makes possible valid com-
parisons of results from samples receiving and not receiving this
treatment. Nevertheless, two alternative extraction procedures
were considered, and tested briefly with Love Canal soil and
sediment samples, before the final choice was made in favor of
modified Method 625.
The two alternative extraction procedures considered were as
follows. First, an extraction procedure using a Isl mixture of
acetone and hexane with the high speed mechanical stirrer was
tested, but qualitatively had no apparent advantages. And sec-
ond, an extraction procedure based on steam distillation that had
been used by the New York State Department of Health for the
analysis of Love Canal samples was also tested briefly. This
method was rejected because it may produce chemical artifacts,
such as nitroaromatic compounds, that are probably formed at the
temperatures required for steam distillation. Other thermally
promoted chemical changes were considered likely, which also made
the method unattractive.
248
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The modified Method 625 selected for the analysis of Love
Canal soils and sediments has not been formally validated in a
multilaboratory study. This same class of compounds may be mea-
sured with other methods which would likely give somewhat differ-
ent results for some analytes. Modified Method 625 is not lim-
ited to the analytes listed in Method 625 (as amended for the
Love Canal study), but will observe any compound structurally
similar to any method analyte and with similar physical and chem-
ical properties. The method is limited to compounds with a
molecular weight from 35 to 450 amu, because that was the limit
of the mass spectrometer scan. The standard reporting units for
modified Method 625 are micrograms per kilogram, and further in-
formation about the method is contained in later parts of this
section.
The great strength of modified Methods 624 and 625 is that
each method provides the complete 70 eV mass spectrum for each
analyte. This, together with the retention index, allows a very
high degree of qualitative accuracy, that is, these methods are
highly reliable in the identification of the method analytes plus
any other analytes that are susceptible to the sample preparation
and chromatographic conditions. Another great strength common to
these methods is their utility with numerous analytes (1 to 100
or more) simultaneously in the same sample. Thus, the methods are
very cost effective. The weakness of both methods is that they
are not the most precise or sensitive mass spectrometric methods
that could be chosen. Methods that use selected ion monitoring,
like that used for 2,3,7,8-tetrachlorodibenzo-p-dioxin, are both
more precise and sensitive, but also more costly to apply when a
large number of analytes are to be measured. The application of
fused silica capillary columns with modified Method 625 may be
considered both a strength and a weakness. The strength is the
high resolution chromatographic performance of the columns, and
the weakness is that the columns are so new that only a limited
number of laboratories had experience in using them. Also, their
availability was limited at the time of the study.
A few of the chlorinated hydrocarbon pesticides were known to
be sensitive to the pH 12 extraction conditions of modified Meth-
od 625, and measurements were desired for certain very toxic pes-
ticides at levels below the detection limits for modified Method
625. (See a later general discussion of detection limits). There-
fore, the chlorinated hydrocarbon pesticides and a few related
compounds (PCBs) were measured using modifications to methods
that are described in Manual of Analytical Methods for the
Analysis of Pesticides in Humans and Environmental Samples, EPA-
600/8-80-038,June,1980.Soilswereextractedbyaprocedure
entitled "Organochlorine Insecticides in Soils and Housedust" in
the aforementioned report, but the extracts were analyzed using
the conditions described in EPA proposed Method 608 as described
in the Federal Register, Vol. 44, No. 233, December 3, 1979, p.
69501.
249
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Briefly, the air dried and sieved soil was extracted in a
Soxhlet apparatus with a Isl mixture of acetone and hexane, the
extract was concentrated, partitioned on alumina and florisil,
and analyzed using a packed gas chromatography column with an
electron capture detector (GC/ECD). Sediments were extracted by
a procedure entitled "Organochlorine and Organophosphorus Insec-
ticides in Bottom Sediment" in the same report, but were again
analyzed with the Method 608 conditions referenced previously.
The sediments were air dried, blended in a mixer with sodium sul-
fate, extracted in a chromatographic column with a 1:1 mixture of
acetone and hexane, and the extract was added to water. The wa-
ter was then extracted in a separatory funnel with 15 percent
methylene chloride in hexane, the extract was concentrated, par-
titioned on florisil, and analyzed with the Method 608 condi-
tions .
It was required that any pesticides identifed by GC/ECD
(Method 608) be confirmed by the analysis of the same extract
with gas chromatography/mass spectrometry using the Method 625
conditions. The complete soils and sediments methods have not
undergone formal multilaboratory validations. The standard re-
porting units are micrograms per kilogram, and further informa-
tion about these methods is contained in later parts of this
section. The soil and sediment GC/ECD method is referred to as
modified Method 608 in the balance of this Appendix.
All elements except mercury were analyzed by either direct
flame aspiration or furnace atomic absorption spectrometry. The
samples were digested with nitric acid and hydrogen peroxide
prior to measurements using the methods described in Methods for
Chemical Analysis forWater and Wastes, EPA-600/4-79-020. For
furnace atomic absorption methods, background correction and cal-
ibration with the method of standard additions was required; for
direct flame aspiration, justification was required to omit cali-
bration by standard additions. Mercury was measured by the cold
vapor atomic absorption procedure as described in Methodsfor
Determination of Inorganic Substances inWater and FluvialSedi-
ments , Book 5, Chapter Al, U.S. Geological Survey, 1979. The
mercury is reduced to the elemental state, aerated from solution,
and passed through a cell positioned in the light path of an
atomic absorption spectrometer. Parts of or all of the methods
for the elements have been validated in multilaboratory studies.
The standard reporting units for elemental measurements are
micrograms per kilogram. More detailed information about the
atomic absorption methods and background correction is presented
in Appendix C, in the section entitled "Methods Selected for
Analysis of Water Samples".
Qua1itati ye Ana1ys es
For those materials named in this report as modified Method
608 analytes, modified Method 624 analytes, modified Method 625
250
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analytes, and metals analytes, the analytical laboratories had
available known concentration calibration standards, and the re-
sults were reported in micrograms per kilogram. However, with
mass spectrometric methods, compounds not on a targeted analyte
list are often detected, and may be identified by their mass
spectra. When observed, these compounds are designated as quali-
tative identifications, but concentrations were not measured be-
cause appropriate calibration standards were not available. In
general, modified Methods 624 and' 625 will observe any compound
structurally similar to any method analyte and with a molecular
weight less than 260 and 450 respectively. Qualitative analyses
were required of the 20 most abundant total ion current peaks in
the chromatogram that were nontarget compounds.
METHODS SELECTED FOR ANALYSIS OF BIOTA SAMPLES
Analytical methods for biota analyses were selected with the
overall goal of the biological monitoring program in mind. This
goal was to provide limited, suggestive indication of the accum-
ulation of substances monitored in biological systems, thereby
potentially increasing the sensitivity of the entire monitoring
program. Therefore, not all target analytes discussed under wa-
ter samples (Appendix C) and soil and sediment samples (previous
section of this Appendix), were determined in all biota samples.
Because the biological monitoring effort was very limited, ana-
lytical methods and quality assurance procedures were selected to
minimize costs and to keep the effort in perspective with the
overall study.
Because of EPA's very limited experience and capabilities in
chemical analyses of biota samples, no pre-study precision, ac-
curacy, or detection limit goals were established. The following
methods were selected as the ones that best met the project
needs.
Mouse, crayfish, and earthworm tissue were analyzed for the
Method 625 analytes (Appendix A) plus the qualitative analytes
described under soils and sediments. The procedure used was an
adaptation of one published in Analytical Chemistry, 1978, 50,
182 (from the EPA Environmental Research Laboratory, Duluth, Min-
nesota) that was intended for high fat content fish tissue. The
adaptation is described in Organics Analysis Using Gas Chroma-
tography-Mass Spectrometry (W. L. Budde and J. W. Eichelberger,
Ann Arbor Science Publishers, Inc., Ann Arbor, Michigan, 1979).
Briefly, in this method frozen tissue samples were blended with
solid carbon dioxide and anhydrous sodium sulfate, and the dried
mixture extracted in a Soxhlet apparatus with a 1:1 mixture of
acetone and hexane. The extract was concentrated to a low volume
and the fatty material was separated from the compounds of inter-
est with gel permeation chromatography. The concentrated eluate
was examined by gas chromatography/mass spectrometry using the
conditions described for modified Method 625 in the soils and
251
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sediments section of this Appendix. This method has not been
validated in a multilaboratory study, and this same class of
compounds may be measured with other methods which would likely
give somewhat different results for some analytes. The standard
reporting units are micrograms per kilogram.
Potatoes and oatmeal were analyzed for halogenated Method 624
analytes. The procedure employed a headspace sampling technique
after digestion of a small sample with hot sulfuric acid in a
sealed container. The headspace gases were analyzed with a
packed gas chromatographic column using a halogen specific Hall
detector. All results from this method must be considered tenta-
tive because they were not confirmed by mass spectrometry or
another spectrometric technique. All concentrations were con-
sidered crude estimates for exploratory purposes because the
method was essentially untested.
Metals were measured in hair from dogs and mice, and in
silver maple tree leaves. Hair was cleaned, digested in nitric
acid, and analyzed using the atomic absorption methods described
in Appendix C. The furnace technique was employed for most metals
except cadmium, where direct aspiration in a flame was permitted,
and mercury, where the cold vapor technique was used.
Metals in vegetation were measured with atomic absorption or
inductively coupled argon plasma (ICAP) emission spectrometry.
Vegetation was digested with nitric and perchloric acid and, in
some cases, sulfuric acid. The instrumental techniques are de-
scribed in Appendix C of this Volume.
METHODS SELECTED FOR RADIOACTIVITY
Soil, sediment, and water samples were examined for radio-
activity. Because the methods used for water samples were very
similar to those used for soil and sediment samples, they were
not described previously in Appendix C.
Soil, sediment, and water samples were collected in 300
milliliter Teflon-lined aluminum cans. The analysis for gamma-
emitting radionuclides was accomplished with a well shielded
computerized gamma ray spectrometer using a solid state high
resolution gamma ray detector (lithium drifted germanium or
intrinsic germanium). This analysis required no sample prepa-
ration, and the samples were not even removed from the sealed
aluminum cans. Because samples were not removed from their con-
tainers, the possibility of laboratory losses or contamination
was essentially eliminated, and the principal quality assurance
activity was a daily instrument calibration and frequent measure-
ments of calibration check samples. All radioactivity measure-
ments were performed by EMSL-Las Vegas. This EPA laboratory is
also responsible for conducting a nationwide quality assurance
252
-------
program for measurements of radionuclides in environmental sam-
ples. All standards used were traceable to the National Bureau
of Standards.
The method detection limit for a given radionuclide is depen-
dent on the abundance of the gamma rays emitted and their energy.
For cesium-137 the detection limit is approximately 50 picocuries
per liter of water and 40 picocuries per kilogram of soil or
sediment. After counting the gamma emissions from drinking water
samples, the containers were opened, the water was distilled, and
an aliquot of the distillate mixed with a liquid scintillating
material. The mixture was then analyzed for tritium by scintil-
lation counting. The detection limit for this procedure is ap-
proximately 300 to 400 picocuries per liter. (See Table 13 and
Section 4.3.3 in the text for additional information).
SELECTION OF ANALYTICAL SUBCONTRACTORS
Details of the analytical subcontractors selection process
are given in the QA/QC summary report on the Love Canal project
prepared by the GCA Corporation. Briefly, the process included:
(1) the provision by EPA to the prime contractor of the names of
a number of laboratories that were known from past or ongoing
environmental monitoring programs to have the generally required
capabilities; (2) technical evaluation criteria were prepared;
(3) proposals were solicited; and (4) a prospective bidders con-
ference was held. The proposals received were reviewed in terms
of the evaluation criteria, which included immediate availability
to initiate analyses, quality assurance plan, experience with
analyses, and availability of appropriate equipment, personnel,
and management. Experience with specific analyses and methods
was examined in detail, and capabilities for handling samples in
a timely manner (and preferences for executing certain methods)
were considered. Finally, cost proposals were considered, but
this was not a compelling factor. One bidder was not selected
because the bid was considered too low to permit the subcontrac-
tor to carry out the analyses with the minimum required quality
assurance program. Because of the urgency of the program and the
deadlines imposed on EPA, there was no time to conduct a preaward
interlaboratory study with actual samples to refine the selection
process.
LIMITS OF DETECTION/QUANTITATION
In Appendix C, it was possible to calculate limits of detec-
tion (LOD) for several methods from subcontractor supplied re-
sults of the analyses of laboratory control standards. A labor-
atory control standard was defined as a solution of analytes of
known concentration in reagent water. By contrast, in the soil,
sediment, and biota media, there are substantial impediments to
the measurement of limits of detection. In particular, it is
very difficult to add a known amount of an analyte or analytes to
253
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a soil, sediment, or biota sample and simulate the natural sorp-
tion or uptake processes. Therefore, known additions (spikes)
are often superficial and do not rigorously test an analytical
method. In the Love Canal project, an attempt was made to devel-
op laboratory control standards based on known additions of ana-
lytes to a common standard media, National Bureau of Standards
(NBS) Standard Reference Material (SRM) 1645, river sediment.
The SRM 1645 contains high levels of a number of organic com-
pounds, but only a few that were on the Love Canal monitoring
list, and none of the concentrations were certified by NBS.
Furthermore, there does not exist a SRM containing certified low
concentrations of appropriate analytes that could be used to
measure limits of quantitation.
Disregarding the superficial nature of the known additions to
NBS sediment, the analyses could have been used to calculate lim-
its of detection except that the concentrations added were far
too high to be applicable to the LOD procedure used for water
analyses (Environmental Science and Technology, 1981, 1426). High
level spikes, in the milligrams per kilogram range, were made be-
cause of the high levels of background in the SRM, and because of
anticipated high levels of contamination in Love Canal samples.
Under these circumstances, no measurements of limits of detection
were possible.
Because modified Methods 608, 624, 625, and the metals meth-
ods are very similar to the methods used in water samples, except
for the extraction of the sample, it is reasonable to estimate
the limits of detection for soil/sediment/biota samples at the
same order of magnitude as those calculated or estimated for the
water samples. The limits of detection for water samples are
given in Tables C-l, C-2, and C-3 in Appendix C, and are de-
scribed and discussed in the section on "Limits of Detection/
Quantitation."
Method detection limits were not used to validate data in the
Love Canal data base. Variability in quantitation and detection
limits among laboratories is well known and unavoidable. Some
laboratories may have quantified substances that others called
"trace" or did not report the substances. These occurrences do
not invalidate the results. At the worst, the method detection
limits were probably several hundred micrograms per kilogram.
Because the conclusions of the study were based on samples con-
taminated at several orders of magnitude or higher concentrations
(that is, parts per million to parts per thousand), the magni-
tudes of the method detection limits had no affect on the overall
conclusions of the study.
ANALYTICAL LABORATORY PERFORMANCE EVALUATIONS
In the soil, sediment, and biota media no specific perform-
ance evaluation (PE) samples were available. Therefore, the
254
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performance of the laboratories was evaluated using the samples
described in Appendix C because: (1) the analytical laboratories
conducting these analyses were often the same laboratories con-
ducting water analyses; (2) the analytical methods were similar
to water methods? and (3) the analyses were conducted over the
same time period.
As pointed out in Appendix C, information from PE samples was
not used to estimate precision and accuracy of the analytical
measurements or to validate data for the Love Canal data base,
because the PE samples were concentrates in an organic solvent
that were added to reagent water by the analytical laboratory
before the application of the method. Therefore, although the
analytical laboratories were unaware of the true concentrations,
they were aware that the samples were PE samples and may have
taken unusual care in their analyses. The purpose of the PE sam-
ples was to discover problems with the execution of the methods
and enable corrective action by the prime contractor on a timely
basis.
For analytical laboratories analyzing soil, sediment, and
biota samples, the PE samples in water did not, and could not,
evaluate performance in the sample preparation parts of the
soil/sediment/biota methods. However, because the remaining
parts of the methodology were very similar (for example, the con-
centration, chromatography, and mass spectrometry), the PE sam-
ples served a useful purpose. In Table C-4 of Appendix C, a sum-
mary is presented of the percentage of acceptable PE results, by
analytical method analyte group and analytical laboratory. In
order to have an acceptable result, the analytical laboratory
must have correctly identified the analyte and measured its con-
centration to within the acceptance limits specified by the Qual-
ity Assurance Branch, IMSL-Cincinnati. The performance of the
laboratories in identifications was generally excellent, with
very few analytes missed. The unacceptable results in Table C-4
were largely due to concentrations measurements outside the ac-
ceptable range. One laboratory shown in Table C-4 (SWRI), analy-
zed only soil and sediment field samples and no water field sam-
ples. As noted previously under methods selected for analysis of
water samples, Method 625 employed the relatively new fused
silica capillary columns, and there was initially some difficulty
in adjusting to this in some laboratories. The PE samples served
to assist in this adjustment and to provide data on the appli-
cability of the columns. The performance evaluation results con-
firmed that the analytical laboratories were qualified users of
th e me thodo1ogy.
It should also be noted that there was an attempt to prepare
PE samples in a solid matrix by known additions of organic anal-
ytes to a common material, the National Bureau of Standards
Standard Reference Material 1645, river sediment. This effort
was not successful because the samples were not homogeneous and
the results could not be used.
255
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SAMPLE PRESERVATION
Directions for sample preservation were included in the ana-
lytical methods referenced previously. For the modified organic
compounds methods (608, 624, and 625), preservation requirements
included shipment and storage of samples in iced or refrigerated
containers. There was a very high degree of compliance with
these preservation requirements.
Maximum sample holding times prior to analysis were also
specified in the methods, and were based typically on the water
samples holding time requirements. There was a relatively high
percentage of samples that were not analyzed within the specified
holding times because the magnitude of the analytical require-
ments of the Love Canal study, plus numerous other ongoing envi-
ronmental studies, literally overwhelmed the national capacity
for low-level chemical analyses. The situation was especially
prevalent with regard to the organics analyzed using modified
Methods 624 and 625, which employ state-of-the-art gas chroma-
tography/mass spectrometry technology, and Method 608. An anal-
ysis of the holding times revealed that most modified Method 608
and modified Method 625 samples were extracted within the 7-day
holding time, and analyzed within the 30-day extract holding
time. However, most modified Method 624 samples were held longer
than the 14-day holding time. It should be noted, however, that
the applicability of this 14-day holding time limit to soil and
sediment samples analyses using modified Method 624 was not known
empirically.
A study was undertaken by EMSL-Cincinnati to determine the
effects of prolonged sample holding times on the stability of
modified Method 624 analytes. Four modified Method 624 samples
that had been analyzed, and then held for 97 days at 4°C and pro-
tected from light (which was considerably longer than the longest
holding time period), were reanalyzed. Only one sample gave some
evidence of losses of benzene and toluene. The conclusion was
that for samples stored from 1 to 60 days before analysis accord-
ing to the instructions in the methods, there was probably no
significant losses of volatile analytes. Therefore, no samples
were invalidated because holding times were exceeded.
DATA VALIDATION PROCEDURES
Validation means the rejection of certain analytical results
whenever there was compelling evidence of systematic errors in
sampling, preservation, or analysis associated with those re-
sults. Data validation for soil, sediment, and biota samples was
rendered particularly difficult because there was so little ex-
perience with the methods. Furthermore, there was either little
(or no) single laboratory or multilaboratory performance data, or
precision and accuracy data. Therefore, lenient validation
standards were established that were based on general principles,
256
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and very few samples were invalidated. For soil samples, a total
of nine samples were rejected by the data validation process,
where obvious errors in methods execution were observed. For
sediment and biota samples, seven samples each were rejected;
again, for obvious errors in methods execution. With all these
media, it was reasoned that it was better to employ conservative
invalidation criteria (leading to but few rejections of results),
rather than risk losing potentially valuable information because
of insufficient experience with the methods.
Modified Methods 624and 625 with Soil and Sediment
For these methods the principal validation tool was a series
of quality control compounds, often called surrogate analytes,
that were added to each sample. The compounds selected as surro-
gates were valid method analytes that were neither commercially
produced nor naturally occurring. Therefore, it was highly un-
likely that any of them would be found in any environmental sam-
ple. The compounds are shown in Table D-l along with the multi-
laboratory mean percentage recoveries, relative standard devia-
tions, and acceptance limits. Analytical laboratories reported
the quantities added (true values) and the amounts measured.
Statistical acceptance limits were computed by EMSL-Las Vegas,
but were used carefully because of the previously mentioned un-
certainties associated with making known additions to solid
matrices.
As was mentioned in the section on Limits of Detection/Quan-
titation, it is very difficult to add a known amount of an ana-
lyte or analytes to a soil, sediment, or biota sample and simu-
late the natural sorption or uptake processes. Therefore, known
additions (spikes) are often superficial and do not rigorously
test an analytical method. Alternatively, a spike may rapidly
and (nearly) irreversibly sorb to a solid particle and the fail-
ure to recover it may not be indicative of laboratory perform-
ance. Therefore, recognizing the limitations of the methods, a
sample was accepted as valid if at least one of the two to four
surrogates used in the sample was reported in agreement with the
acceptance limits in Table D-l. A minimum surrogate recovery of
1 percent was often considered acceptable, but occurred rarely.
Only one of 452 samples analyzed by modified Method 624 was in-
validated. With modified Method 625, 15 samples were invalidated;
13 of these samples were from CMTL. In all cases, these samples
were invalidated because surrogates were either not reported or
recoveries were so high that major method execution errors were
suspected.
Laboratory Contamination
Methylene chloride was the solvent used in modified Method
625, and it was an analyte in modified Method 624. Methylene
chloride was reported as the only analyte in a large number of
257
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TABLE D-l. SUMMARY STATISTICS AND ACCEPTANCE
LIMITS FOR MODIFIED METHOD 624 AND MODIFIED METHOD 625
SURROGATES FROM ALL LABORATORY MEASUREMENTS
Surrogate
Analyte
Method 624 — modified
Carbon tetrachloride- C
Carbon tetrachloride- C
1 » 2-Dichloroethane-D .
1 , 2-Dichloroethane-D4
Toluene-D0
o
Toluene-Dg
4-Chlorotoluene-D4
4-Chlorotoluene-D
Fluorobenzene
4-Bro»nof luorobenzene
Method 625— modified
Hexachlorobenzene- C.
Hexachlorobenzene- C,
D
Tetrachlorobenzene- C^
Tetrachlorobenzene- C,
4-Chlorotoluene-D4
4-Chlorotoluene-D4
Pentachlorophenol- C,
Pentachlorophenol- C-
2-Fluorophenol
1-Fluronaphthalene
4,4' -Dibromooctof luoro-
biphenyl
Nitrobenzene-D_
Phenol-D.,
Sample
Type
soil
sediment
soil
sediment
soil
sediment
soil
sediment
soil
soil
soil
sediment
soil
sediment
soil
sediment
soil
sediment
soil
soil
soil
sediment
sediment
Mean
Recovery
(Percent)
99
82
68
67
97
102
87
81
93
95
56
46
51
68
21
41
22
37
57
69
62
48
47
Relative
Standard
Deviations
(Percent)
26
33
29
15
13
17
23
28
14
4.2
64
89
55
56
119
56
112
103
54
62
60
67
70
Acceptance
Limits
(Percent)
,47-151
28-136
28-108
47-87
72-122
68-136
47-130
35-127
68-118
87-103
1-128
1-128
1-107
1-144
1-71
1-87
1-76
1-113
1-119
1-155
1-136
1-112
1-113
258
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reagent and field blanks, and in many modified Method 624 samples
it was the only analyte detected. This evidence strongly sug-
gested the occurrence of laboratory contamination which was not
unexpected with such highly sensitive analytical methodology.
Therefore, although a few reports of methylene chloride may have
been valid, the overwhelming number were very likely laboratory
contaminants and it was impossible to distinguish the former from
the latter. Therefore, all reports of methylene chloride in
modified Method 624 samples were deleted from the data base to
maintain the integrity of the study.
Late in the data reporting period, after this methylene
chloride problem was discovered, one of the laboratories was in-
spected by EPA personnel. A large opening was found in the lab-
oratory between the area where the methylene chloride extractions
were conducted and the room where the analytical instrumentation
was located. This finding supported the strong probability that
methylene chloride was a laboratory contaminant in at least one
of the laboratories.
Di(2-ethylhexyl)phthalate is a plasticiser used in the formu-
lation of many plastic articles common to analytical laborato-
ries, and was detected in widely varying amounts in both reagent
blanks and field blanks. Therefore, all reports of this compound
were judged highly unreliable and all reports were removed from
the validated data base.
Modified Method 608 with Soil and Sediment
For this method the principal validation tool was the re-
quirement that a laboratory control standard was to be analyzed
with each batch of samples processed in a group at the same time.
A laboratory control standard (LCS) was a known addition of three
method analytes to a common matrix, the previously discussed NBS
SRM river sediment 1645. The uncertainties associated with known
additions to solid matrices, which were discussed in the previous
section, were also applicable to this method. The three analytes
were heptachlor, aldrin, and dieldrin, which are chlorinated hy-
drocarbon pesticides. Recoveries of these from the LCS matrix
averaged 77 to 101 percent, depending on the laboratory, and the
acceptance limits were in the range of 20 to 150 percent. No
samples were invalidated by this procedure.
Modified Method 608 employs an electron capture gas chroma-
tographic detector, and is subject to false positive identifica-
tions. In order to minimize these, two column confirmation and
gas chromatography/mass spectrometry (GC/MS) confirmations were
required for all modified Method 608 results. However, GC/MS
confirmation was limited by the difference in detection limits
between the methods. Users of the Love Canal data should be
aware of the probability that low level, less than 0.5 micrograms
per kilogram, measurements by modified Method 608 were not con-
firmed by GC/MS.
259
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Metals in Soil and Sediment
As with modified Method 608, laboratory control standards
(LCS) consisting of known additions (spikes) to the common ma-
trix, NBS SRM river sediment 1645, were required. Again, the
uncertainties of the spiking procedure were present. The NBS
sediment contained metals analytes, but did not contain the four
Love Canal analytes barium, beryllium, selenium, and silver.
Therefore, known additions were required, and some known addi-
tions to real Love Canal samples were included in the quality
assurance program. Each laboratory analyzed 10 LCS samples
initially, then another LCS or a spike of a Love Canal sample for
every 10 environmental samples. The laboratories were required
to measure the background levels first and subtract these from
the spike concentrations before the percentage recoveries were
computed.
An overall mean recovery was calculated for each metal using
the results from all laboratories. The means were in the range
of 82 to 112 percent generally, the only exceptions being 64 per-
cent for antimony and 77 percent for selenium in laboratories
analyzing soil samples. A mean standard deviation of 18.5 per-
cent of the mean recoveries was calculated for all laboratories,
all metals, and both sample types (soil and sediment). Two times
this standard deviation or 37 percent was used as the acceptance
criterion for LSC samples and known additions to Love Canal sam-
ples. If any given measurement of any metal in an LCS or sample
spike exceeded the limit of the metal's overall mean recovery
plus or minus 37 percent, that metal measurement was invalidated
in all samples associated with the particular LCS or sample
spike. Thus, a sample could have an invalid recovery for one or
several metals but be valid for the remainder of the metals. A
total of 49 individual metals measurements were invalidated with
more than 90 percent of the occurrences involving antimony, ar-
senic, selenium, and silver.
Method 625 Ana1ytesin Biota
Only a minimal data validation effort was made for the rea-
sons given in the section entitled, "Methods Selected for Ana-
lysis of Biota Samples," and very few samples were invalidated.
However, isophorone was identified as a possible artifact created
by the use of acetone during extraction of samples. Suspicions
were aroused when this compound was found in many biota samples
but not in any soil and in only one sediment sample. The GCA
Corporation was requested to investigate this problem. Their re-
port indicated that soxhlet extraction with acetone under certain
pH conditions can result in the formation of several condensation
products such as mesityl oxide, phorone, and isophorone. Consid-
ering that diacetone alcohol, mesityl oxide, and phorone were
identified in the extracts, and the half-life of isophorone in
260
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the environment is approximately 1 month, and therefore not like-
ly to have persisted in the environment over the period since the
Love Canal landfill was closed, it was concluded that isophorone
was an analytical artifact. Because of these reasons, isophorone
in biota samples was removed from the Love Canal data base. It
is not certain, of course, that the half-life of isophorone is or
is not so short when stored in biological tissues.
Metals in Hair and Vegetation
The same data validation procedures described for metals in
soil and sediment were employed for metals in hair. A total of
48 individual measurements (26 for mice, 22 for dogs) were in-
validated; virtually all occurrences involved copper.
The National Bureau of Standards SRM orchard leaves was used
as the laboratory control standard for the single laboratory that
measured metals in vegetation. The criteria for validation were
the same as described under soils and sediments, but all results
for antimony, beryllium, chromium, and selenium were invalidated
because all LCS samples gave zero percent recoveries.
ESTIMATES OF DATA PRECISION
The purpose of the field triplicate samples described at the
beginning of the data validation section in Appendix C was to
establish interlaboratory and intralaboratory precision. In ad-
dition, some methods required taking two aliquots of 10 percent
of the samples to obtain further information about intralabora-
tory precision. However, a high percentage of the total samples
gave all analytes below detection limits, and insufficient infor-
mation was available to estimate the precision of the measure-
ments from these samples.
Data precision may be estimated using the results of the
measurements of the laboratory control standards (LCS) that were
described in the section entitled "Limits of Detection/Quantita-
tion." It should be noted that this is a less desirable approach
than using field triplicate samples, because the LCS measurements
do not include the variability associated with sampling, trans-
portation, storage, and preservation of samples. Also these data
may have been obtained over a period of weeks by some laborato-
ries, and the values may include week-to-week variations that may
significantly exceed variations within a given analysis day.
Nevertheless, lacking the information from the replicate field
samples, the LCS measurements may be used to provide rough esti-
mates of data precision.
Table D-2 shows the relative standard deviations for repli-
cate measurements of modified Method 624, modified Method 625,
and modified Method 608 analytes in LCS samples. Note that sum-
mary statistics are reported in the table only when at least
three replicate measurements were available. Some laboratories
261
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TABLE D-2. RELATIVE STANDARD DEVIATIONS (RSD) FOR ORGANIC
ANALYTES IN LABORATORY CONTROL STANDARDS NBS SEDIMENT
Analytical Laboratory
Analyte
Method 624 — modified
Benzene
Toluene
Chlorobenzene
Method 625 — modified
2-Chlorophenol
4-Chloro-3-methylphenol
Pentachlorophenol
4-Nitrophenol
1 , 4-Dichlorobenzene
N-nitrosodi-n-propylamine
1,2, 4-Trichlorobenzene
2 , 4-Dinitrotoluene
Di-n-butylphthalate
Pyrene
Benzo( a ) anthracene
Benzo( b ) f luoranthene
Benzo(a)pyrene
Indeno( 1,2 ,3-cd)pyrene
Benzo(g,h, i, )perylene
Method 608 — modified
Heptachlor
Aldrin
Dieldrin
Aroclor 1242
ACEE
16
11
14
45
58
37
58
48
65
60
77
19
53
84
62
48
69
58
14
61
37
—
CMTL GSRI
16 47
14 10
15 19
105
117 117
123
—
77
114
81
103
87
121
—
—
—
—
—
15 45
16 20
29 19
58
SWRI
16
13
14
31
44
68
114
67
28
35
55
24
—
--
—
—
—
—
11
12
8.3
—
Code
EMSL-Cin
5.8
5,3
13
--
__
__
__
—
__
—
—
—
—
__
—
__
—
—
--
—
--
262
-------
did not analyze a sufficient number of some types of samples to
accumulate the minimum required number of LCS measurements to
justify computing summary statistics. The precision of any
single measurement in the Love Canal data base at the 95 percent
confidence level may be estimated using the formula:
Analytical Result + 1.96 x (RSD from Table D-2).
The RSD should be selected from Table D-2 according to the ana-
lyte measured and the laboratory analyzing the sample. If the
exact analyte is not in Table D-2, a structurally similar analyte
may be used; for example, if the analyte of interest is 2-
nitrophenol, the RSD for 4-nitrophenol may be used. If RSD data
for a reporting laboratory of interest is not in Table D-2, use
TABLE D-3. RELATIVE STANDARD DEVIATIONS (RSD) FOR METALS
ANALYTES IN LABORATORY CONTROL STANDARDS NBS SEDIMENT
Analyte
Arsenic
Antimony
Barium
Beryllium
Cadmium
Chromium
Copper
Lead
Mercury
Nickel
Selenium
Silver
Thallium
Zinc
Analytical
ERGO
12
9.4
9.4
7.3
3
8.8
2
7
17
3.1
7.2
4.7
4
4.9
Laboratory
PJBL
47
79
44
19
7
27
25
32
18
15
51
13
28
16
Code
SWRI
10
74
12
8.7
2
12
13
3
9
6.4
4.6
39
7.2
3
263
-------
the mean RSD of all laboratories reporting that analyte. For
metals and anions a similar estimate may be made using the data
in Table D-3.
Precision estimates were not used to validate data for the
Love Canal data base. Data validation procedures are explained
in detail in the previous section entitled, "Data Validation
Procedures."
ESTIMATE OP DATA ACCURACY
Data from modified Methods 624, 625, and 608 for organic
analytes probably have a significant bias, but this cannot be
estimated because suitable standard reference materials were not
available. The limitations of using known additions for this
purpose were explained in detail previously.
For metals measurements several SRMs were available, but they
did not contain all the analytes of interest. Table D-4 shows
the mean percentages of the NBS certified values in SRM river
sediment 1645 observed by the analytical laboratories, and the
computed standard deviations. These values were not used direct-
ly to validate data for the Love Canal data base, but do indicate
TABLE D-4. MEAN PERCENT RECOVERIES AND STANDARD DEVIATIONS
OF NBS CERTIFIED VALUES IN SRM RIVER SEDIMENT 1645
Analytical Laboratory Code
ERGO
Analyte
Arsenic
Antimony
Cadmium
Chromium
Copper
Lead
Nickel
Thallium
Zinc
Mean
103
47
84
105
99
102
90
—
96
S.D.
11
43
8
7
5
8
12
—
6
PJBL
Mean
113
112
90
78
94
86
90
104
78
S.D.
55
64
15
5
2
12
13
—
4
SWRI
Mean
66
6
89
105
91
93
68
93
92
S.D.
16
6
4
9
4
4
10
80
2
S.D.: Standard Deviation
264
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the difficulties encountered in the measurement of arsenic, anti-
mony, and a few other elements at some laboratories. As indicat-
ed previously, measurements of these elements were selectively
invalidated. For most of the other elements there was no signif-
icant bias in the metals measurements in river sediment.
SUMMARY OF MAJOR ACTIONS TAKEN AS A RESULT OF GCA'S QUALITY AS-
SURANCE FUNCTION
The activities of the prime contractor in the day-to-day
quality assurance program are described in detail in the GCA
QA/QC summary report on the Love Canal study. The purpose of
this section is to briefly summarize major actions by the GCA
Corporation.
The prime contractor routinely discussed, by telephone and
during site visits, the results of the external quality assurance
samples with the analytical laboratories. Requirements for cor-
rective action were provided during these discussions. The prime
contractor also monitored the results from the internal quality
assurance program, and discussed these with the analytical lab-
oratories during telephone conversations and site visits. Again,
requirements for corrective action were provided.
One significant action that resulted from the day-to-day
quality assurance program was the removal of the PJBL laboratory
from the analyses of samples by modified Method 625 in soils and
sediment. During a site visit and during discussions of the in-
ternal and external quality assurance samples, it was discovered
that PJBL was using packed columns with modified Method 625, and
did not have the capability to analyze the samples with the fused
silica capillary columns. Consequently, all previous results
using modified Method 625 provided by PJBL were removed from the
Love Canal data base, and work on modified Method 625 was sus-
pended at PJBL. Eventually, PJBL developed the capability to use
the fused silica capillary columns and all the extracts were re-
analyzed. Details of this incident and other activities of the
prime contractor are given in the GCA Corporation QA/QC summary
report referenced previously.
265
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APPENDIX E
QUALITY ASSURANCE FOR AIR SAMPLES
OVERVIEW OF QUALITY ASSURANCE PROGRAM
It was recognized during the early planning stages of the
study that a comprehensive quality assurance (QA) effort would be
required to support the Love Canal monitoring program. Conse-
quently, QA procedures were developed and implemented as an in-
tegral part of the program. This appendix summarizes the quality
assurance efforts for the air portion of the Love Canal monitor-
ing study. Detailed descriptions of the quality assurance and
quality control (QA/QC) procedures used during the collection and
analysis of air samples are contained in the previously refer-
enced Quality Assurance Plan, Love Canal Study,LC-1-619-206 com-
piled by the GCA Corporation, and available from NTIS. Appendix A
to the quality assurance plan describes the sampling procedures,
Appendix B describes the analytical procedures, and Appendix Q
describes the QA plans submitted by the subcontractors used in
this program. A more detailed -discussion of the QA/QC results of
the prime contractor's (GCA Corporation) and the subcontractors'
quality assurance efforts is contained in Love Canal Monitoring
Program, GCA QA/QC Summary Report, available from NTIS. A listing
of compounds and metals to be identified quantitatively or quali-
tatively by each method of analysis is given in Appendix A, Table
A-2.
Because the methodologies selected for use in Love Canal air
analyses had not yet been used routinely in monitoring networks,
the quality assurance program was designed to minimize variabil-
ity in the data and to fully document the precision and accuracy
of the measurements performed during the Love Canal study. In
order to accomplish these goals, the air monitoring and quality
assurance programs were designed by EPA and performed under con-
tract by the prime contractor and the sampling and analysis sub-
contractors. The contracts specified the methods of sampling and
analysis, including quality control steps to be used by the sub-
contractors, and emphasized the importance of quality assurance
by requiring the submittal and approval by EPA of an acceptable
quality assurance plan. The format and content of minimally ac-
ceptable quality assurance plans was developed by EPA and speci-
fied in writing in each subcontract.
266
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In addition to the required QA plans, the following elements
were included in the design of the Love Canal study that were in-
tended to minimize measurement variability.
1. Equipment used to collect air samples was supplied by EPA.
The equipment had been used previously to collect air sam-
ples similar to those collected at Love Canal. The equip-
ment was verified to be in working order prior to ship-
ment.
2. Only one subcontractor was responsible for the collection
of air samples. As a result, all required sampling pro-
cedures were consistently applied across all sampling
sites.
3. Materials used to collect air samples were manufactured
from a single lot and supplied to the field sites. Both
TENAX tubes and polyurethane foam (PPOAM) plugs were
cleaned by a single subcontractor and verified by EPA as
being acceptable for use prior to their being used for
field sampling, calibration standards samples, calibration
check samples, field blanks, or blind audit quality assur-
ance samples. High-volume (HIVOL) filters from the batch
used in the SLAMS monitoring network were used at Love
Canal.
4. TENAX calibration check samples were prepared by a single
subcontractor, and PFOAM calibration check samples were
prepared by EPA. These samples were subsequently supplied
to each analytical subcontractor. Evaluation of analyti-
cal performance during the Love Canal study was based on
common samples analyzed by each laboratory.
5. Common calibration samples were supplied to all laborator-
ies analyzing TENAX tubes.
6. The use of laboratory control charts to monitor measure-
ment system variability and maintain acceptable perfor-
mance was required. Initial control chart limits for
TENAX measurements were specified based on an estimate of
expected performance recommended by an experienced, inde-
pendent laboratory not involved in the Love Canal study.
The actual results obtained from the analysis of calibra-
tion check samples, however, were used to subsequently
establish control limits that were applicable directly to
the laboratories performing the analyses.
Prior to initiation of the monitoring and analysis efforts it
was realized that 1 or 2 months -might elapse before EPA would
receive data that had been subjected to all of the required qual-
ity control checks and verifications. Because of the length of
267
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time that might elapse, it was apparent that timely corrective
actions for problems which were uncovered would be precluded..
Therefore, EPA required, as part of the external QA program, the
analysis of sufficient numbers of calibration check samples and
blind audit samples to allow classification of the precision and
accuracy of subcontractor measurements, which was independent of
the quality control efforts of the sampling and analysis labora-
tories. Because this extensive external program existed, EPA
retained the responsibility for final validation of the analyti-
cal results, and determination of the precision and accuracy of
the air measurements performed at Love Canal.
Carrying out the monitoring effort at Love Canal was the re-
sponsibility of the prime contractor. As part of their efforts
they:
1. Coordinated the distribution of samples to the field sam-
pling sites and subsequently to each analytical subcon-
tractor .
2. Inserted external quality control samples (blanks, blind
audit samples, etc.) into the normal shipments of field
samples in a manner such that they could not be identified
as control samples by analytical laboratories,
3. Supplied calibration and, calibration check samples to the
analytical laboratories.
4. Maintained the day-to-day overview of the sampling, anal-
ysis, and quality control efforts of the subcontractors
through review of data received, and by conducting inspec-
tions at the subcontractor laboratories.
5. Performed the initial verification of data transmitted to
EPA to assure that the reported analytical results were
those actually obtained.
More detailed descriptions and discussions of the GCA Corporation
QA/QC efforts are contained in the previously mentioned docu-
ment (Love Canal Monitoring Program, GCA QA/QC SummaryReport),
and are summarized in the last section of this Appendix.
In order to obtain consultation and advice from an indepen-
dent group, the QA plans and results of the Love Canal study were
reviewed by the sampling protocols study group of EPA's Science
Advisory Board. Their review was conducted during the design,
study, and data evaluation phases of the project.
The remainder of this Appendix describes the external quali-
ty assurance program and presents the estimates of data precision
and accuracy for the air samples collected at Love Canal.
268
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METHODS SELECTED FOR ANALYSIS OF AIR SAMPLES
The volatile organic compounds were collected by sorbtion
onto a TENAX cartridge, thermally desorbed, and analyzed by gas
chromatography/mass spectrometry (GC/MS). The method used for
collecting and analyzing volatile organics in air represents the
latest application of research developments in this field. This
method was used because it was the only known technique that
would provide information (at a reasonable cost) on a wide vari-
ety of volatile organics in air, could be used in a routine net-
work operation, and was available at the time required for per-
forming the Love Canal study. The methodology was based on the
work performed by E. D. Pelizzari of Research Triangle Institute
for EPA and other federal agencies. (See References 1 through
7).
Pesticides and related compounds (subsequently referred to
as pesticides in the remainder of this Appendix) were collected
on polyurethane foam plugs (PFOAM). PFOAM collectors were ana-
lyzed by Soxhlet extraction, followed by sample concentration and
gas chromatography. High performance liquid chromatography was
used for the analysis of chlorinated phenols. The methodology
for PFOAM collection of pesticides was developed, in part, by the
Analytical Chemistry Branch, HERL-RTP. (See References 8 through
14) . This sample collection methodology also represented the
latest application of research developments in the field. The
method employed has been extensively tested at HERL-RTP for com-
pounds of interest, and was deemed the most efficient and cost-
effective means available for monitoring pesticides and related
compounds at Love Canal. The PFOAM procedure was a valuable com-
plement to TENAX, because it was used to collect and analyze for
those less volatile compounds that do not thermally desorb effi-
ciently from TENAX for GC/MS determination.
The methodology used to collect air particulate samples
(HIVOL) for metals analyses was the Reference Method for the
Determination of Suspended Particulates in the Atmosphere (High
Volume Method) Code of Federal Regulations (CFR), Title 40, Part
50, Appendix B. HIVOL filters were extracted with an acid mix-
ture and most metals were analyzed by an Inductively Coupled Ar-
gon Plasma Optical Emission Spectrometer (ICAP) technique. Ar-
senic, cobalt, and chromium were analyzed by a Neutron Activation
Analysis (NAA) procedure, directly using the HIVOL filters. These
methods have been used routinely to analyze samples collected in
the EPA National Air Surveillance Network (NASN). The precision
and accuracy of these methods have been documented during their
use in NASN (unpublished data are available from the Environmen-
tal Monitoring Division, EMSL-RTP).
?.69
-------
SELECTION OF ANALYTICAL SUBCONTRACTORS
Because the methodologies for analysis of volatile organics
and pesticides were relatively new, no detailed history of per-
formance of potential analytical subcontractors was available.
In order to acquire an estimate of the capabilities of the ana-
lytical community, a short analytical performance evaluation ex-
ercise was conducted before awarding the analytical contracts for
the Love Canal study. Interested organizations were invited to
Love Canal to collect and analyze volatile organic compounds and
pesticides at a common site. In addition to the field samples,
spiked quality assurance (QA) samples were supplied to each par-
ticipant in this performance evaluation. The results of the anal-
yses of the QA and field samples were used to judge the analyti-
cal capabilities of potential subcontractors and eliminate poor
performers from further consideration. Final subcontractor se-
lection was also based on the number of samples that the subcon-
tractor could analyze during the project period, and the cost of
such analyses.
The metals analyses were all performed by the Environmental
Monitoring Division, EMSL-RTP, using techniques employed on the
NASN samples. Because a history of performance was available, no
pre-Love Canal performance evaluation analyses were required.
LIMITS OF DETECTION/QUANTITATION
Because the methods for collecting and analyzing volatile
organic compounds and pesticides are still undergoing evaluation
as to precision, accuracy, sensitivity, and other parameters,
each analytical subcontractor was asked to provide estimates of
their limit of detection (LOD). A limit of quantitation (LOQ),
based on estimated detection limits, was selected by EPA for each
type of analysis, so that all analytical subcontractors would be
reporting results in the same range. For the parameters being
quantified on TENAX, it was decided that values above 50 nano-
grams per sample (ng/sample) would provide meaningful quantita-
tive results; for pesticides samples, quantitative results were
reported when compounds were above 90 micrograms per plug ( ^g/
plug). Samples yielding measurement signals that were above the
detection limit but below the quantitation limit were assigned
the value trace. As part of the monitoring program, a number of
targeted organic compounds were also to be identified whenever
present in a sample, but not quantified. When these compounds
were identified in a sample at levels above the contractor sup-
plied estimated limit of detection they were labeled "qualita-
tive." All concentrations reported for TENAX and PFOAM analyses
are reported in units of micrograms per cubic meter (jjg/m ). The
estimated limits of detection and quantitation for each parameter
analyzed in the air samples are presented in Tables E-l (TENAX)
and E-2 (PFOAM).
270
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TABLE E-l. VOLATILE ORGANICS ON TENAX
Detaction/Quantitation
Limits (ng/tube)
BCL
Compound
Benzene
Carbon tetrachloride
Chlorobenzene
o-Chlorotoluene
p-Chlorotoluene
1 , 2-Dibromoethane
o-Dichlorobenzene
p-Dichlorobenzene
1,1,2, 2-Tetrachloroethylene
Toluene
1,2, 3-Trichlorobenzene
1,2, 4-Trichlorobenzene
1,3, 5-Trichlorobenzene
Chloroform
1 , 2-Dichloroethane
2 , 4-Dichlorotoluene
o-Chlorobenzaldehyde
p-Chlorobenzaldehyde
Benzyl chloride (a-Chlorotoluene)
1 , 1-Dichloroethane
1 , 1-Dichloroethylene
1 , 2-Dichloroethylene
Dichlorome thane
Phenol
o-Xylene
m-Xylene
p-Xylene
D
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
5
Q
50
50
50
50
50
50
50
50
50
50
50
50
50
Qual.
Qual.
Qual.
Qual.
Qual.
Qual.
Qual.
Qual.
Qual.
Qual.
Qual.
Qual.
Qual.
Qual .
PEDCo
D
3
20
5
4
4
13
7
7
15
6
NA
NA
NA
20
15
7
25
25
25
7
15
15
15
30
5
5
5
Q
50
50
50
50
50
50
50
50
50
50
NA
NA
NA
Qual.
Qual.
Qual.
Qual
Qual.
Qual.
Qual.
Qual.
Qual.
Qual.
Qual .
Qual.
Qual.
Qual .
NA: Not analyzed
Qual.: Only qualitative reporting required
271
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TABLE E-2. PESTICIDES ON FOAM PLUGS
Detection/Quantification
Limits (^g/plug)
GSRI
SWRI
Compound
D
Q
D
Q
Lindane
Hexachlorobenzene
Hexachlorocyclopentadiene
1,2,3, 4-Tetrachlorobenzene
1,2, S-Trichlorobenzene
1,2, 4-Trichlorobenzene
1,3, 5-Trichlorobenzene
2, 4, 5-Trichlorophenol
Pentachlorobenzene
Hexaehloro-1 , 3-butadiene
1,2,4, 5-Tetrachlorobenzene
a, a, 2 , 6-Tetrachlorotoluene
Pentachloro-1 , 3-butadiene
Pentachloronitrobenzene
1,2,3, 5-Tetrachlorobenzene
o-BHC
Heptachlor
30
30
30
30
30
30
30
30
30
30
30
30
30
30
30
30
30
90
90
90
90
90
90
90
90
90
Qual.
Qual.
Qual .
Qual.
Qual.
Qual.
Qual.
Qual.
45
45
45
45
45
45
45
45
45
45
45
45
45
45
45
45
45
90
90
90
90
90
90
90
90
90
Qual.
Qual.
Qual.
Qual.
Qual.
Qual.
Qual.
Qual.
Qual.: Only qualitative identification required
Limits of detection for the metals analyses had been deter-
mined over a period of time by EMSL-RTP prior to the Love Canal
study. These limits are based on analyses of HIVOL filter blanks
and are presented in Table E-3. Because only one laboratory ana-
lyzed samples for metals, quantitative results were reported
whenever the value was above the .limit of detection.
In order to verify limits of detection and to establish
background levels for the TENAX analyses, blank sample tubes were
analyzed throughout the study by the subcontractors. Cleaned
blank TENAX sample tubes were sealed and sent to the field sites.
The tubes were returned unopened to the analytical laboratories
for analysis. The analysts were unable to distinguish these
field blanks from normal samples. The analytical results for
these field blanks are shown in Table E-4. The mean and standard
deviation reported in Table E-4 are for those samples where con-
centrations were above the limit of quantitation (50 ng).
272
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TABLE E-3. DETECTION LIMITS FOR INORGANICS
(HIVOL SAMPLES)
Element
sample
Antimony
Arsenic
Beryllium
Cadmium
Chromium
Copper
Lead
Nickel
Zinc
26.5
16.2
0.332
0.955
22.2
10.5
28.2
2.56
353.0
TABLE E-4,
RESULTS FROM ANALYSES OF BLANK TENAX SAMPLES'
Number of Number of
Samples With Samples
Quantifiable Listed as
Compound Amounts Trace
Benzene
Toluene
1, 1,2,2-Tetra-
chloroethylene
Carbon
tetrachloride
Chlorobenzene
o-Chlorotoluene
p-Chlorotoluene
1 , 2-Dibromoethene
o-Dichlorobenzene
p-Dichlorobenzene
18
31
62
2
0
0
0
0
0
0
108
82
40
1
1
0
0
1
1
0
Standard
Mean?- Deviation^
3.10 1.31
8.20 6.90
6.17 5.08
3.60 0.92
— --
__
__
__
—
__
^A total of 132-blank samples were analyzed.
*Units are f^g/m and are based on samples with quantifiable
amounts only.
273
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Benzene, toluene, and 1,1,2,2-tetrachloroethylene were re-
ported as present in the vast majority of blank TENAX tubes (for
example, benzene results were reported at concentrations above
the detection limit in 126 of the 132 blanks). All laboratories
identified these compounds as being present. The quantifiable
results for toluene, however, came mostly from one laboratory (29
of the 31 quantifiable results). Consideration of the levels and
variability of benzene, toluene, and 1,1,2,2-tetrachloroethylene
found in the blanks should be made in any interpretation of the
air TENAX results. Toluene and benzene are known normal contami-
nants of TENAX, and their presence at low levels was expected.
An inspection of the facility used for cleaning and preparing the
TENAX prior to field sampling indicated that 1,1,2,2-tetrachloro-
ethylene could have been introduced as a contaminant at that
time.
Analysis of the field data for the compounds benzene, tolu-
ene, and 1,1,2,2-tetrachloroethylene must take into account the
probability that a single result could have been caused by con-
tamination on a blank tube. To be relatively certain that an ob-
tained single value was not due to blank contamination, the field
concentration should be greater than two standard deviations
above the mean values reported in Table E-4 for these three com-
pounds. While it is true that values of benzene, toluene, and
1,1,2,2-tetrachloroethylene that are just above the stated quan-
titation limits could be attributed to blank contamination, the
higher levels monitored at Love Canal should not have been caused
by such contamination. No adjustments for contamination were made
in reported TENAX analyses.
Analyses of field blanks for the PFQAM and metals samples re-
vealed no blank contamination was present. Therefore, values
above the quantitation limits were probably riot caused by blank
contamination.
ANALYTICAL LABORATORY PERFORMANCE EVALUATIONS
In addition to the pre-award evaluation of potential ana-
lytical contractors, two types of performance evaluations were
conducted during the Love Canal project. First, EPA performed
audits at the beginning of the study of the flow rates of the
samplers used for collecting air samples, in order to verify that
the sample collection was being conducted properly. A team con-
sisting of EPA personnel independently measured the flow rates of
several samplers for each type of sampler (TENAX, PFOAM, and HI-
VOL). The results of the audit (reported later under "Estimates
of Data Accuracy") indicated excellent performance by the sam-
pling contractor and no additional flow audits were conducted by
EPA during the 3-month sample collection period. And second, an-
alytical performance was evaluated on a continuing basis through-
out the study. Blind performance evaluation (audit) samples were
periodically sent to each analytical laboratory. These samples
274
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were prepared by an independent contractor (TENAX and metals) or
by EPA (PFOAM) and inserted into the regular field samples by the
GCA Corporation. The analyst was unable to distinguish these
samples from the routine field samples. Results of the analysis
of these audit samples are also discussed later in the "Estimates
of Data Accuracy" section.
SAMPLE PRESERVATION
In order to ensure that valid samples were received at the
analytical laboratories, several precautions beyond the normal
chain-of-custody procedures were taken in the handling of certain
air samples. First, TENAX and PFOAM samples were maintained at
4° C before and after sampling in order to minimize sample degra-
dation. Second, it is known that the TENAX substrate tends to
form artifactual benzene and toluene if left standing for long
periods of time after cleaning. In order to circumvent this
problem, TENAX samples were required to be analyzed within 30
days of final cleaning. Consequently, TENAX was cleaned in
batches during the Love Canal Study, checked by EPA for purity,
and shipped directly to Love Canal. Prudent actions by GCA
Corporation personnel ensured that analyses were accomplished
within the 30-day period. Third, in several instances clean
TENAX tubes were removed from service prior to sample collection,
because the GCA Corporation sample bank coordinator at Love Canal
determined that analyses could not be performed within the 30-day
period. And fourth, HIVOL samples were shipped in such a fashion
that collected particles would not be lost from the filters,
using procedures outlined in the EPA Quality Assurance Handbook
for Air Pollution Measurement Systems, Volume II, Section 2.2.
DATA VALIDATION PROCEDURES
For the volatile organic compounds analyzed from the TENAX
samples, EPA incorporated a scheme for final data validation in
the contractual requirements of the analytical subcontractors.
Special standards, calibration check samples, were supplied to
each analytical laboratory and were analyzed during the first 4
hours of each day's analytical activities, and periodically
thereafter. These samples were supplied and analyzed in addition
to calibration samples and other internal samples which were ana-
lyzed for quality control purposes. The samples were prepared by
the TENAX quality assurance contractor using procedures described
in References 2, 3, 5, and 6. The analytical subcontractor and
GCA Corporation were supplied with true concentrations of these
samples. Both the analytical subcontractor and GCA Corporation
were to monitor the results of the analyses of these samples on a
real-time basis in order to determine if the analysis process was
in control. EPA also attempted to monitor these results during
the analysis period, but results were usually received too late
after the analysis in order for EPA to effectively alter poor
275
-------
performance on a real-time basis. The last section of this Ap-
pendix describes the nature of real-time corrective actions based,
on the GCA Corporation's monitoring of the results from calibra-
tion check samples.
EPA was, however, able to use the results from the analysis
of the calibration check samples as its main data validation pro-
cedure. The results from the calibration check samples were
plotted in a control chart format (percent difference from true
value) after all results had been reported to EPA for each sub-
stance analyzed. The reported results were included from all
analytical systems and the data analyzed as a whole. For each
substance analyzed, +2
-------
Metals data were validated from the analyses of the perform-
ance evaluation samples analyzed as blind unknowns, or from the
analysis of National Bureau of Standards (NBS) Standard Reference
Materials (SRM). The percent difference of the analytical result
from the spike or true value was determined. The results are
shown in the section "Estimates of Data Accuracy." No metals
data were invalidated due to poor analytical performance.
ESTIMATES OF DATA PRECISION
To determine method precision, several field sites were se-
lected for collocating samplers. One of the samplers was desig-
nated the official sampler for the site and the other was desig-
nated the duplicate sampler. The duplicate samples obtained were
then carried through the analysis procedures in the normal man-
ner. The analysts were unable to identify the samples as being
duplicates. The concentration differences (duplicate minus offi-
cial) between the results from collocated samples was used to
estimate the precision of the monitoring data. Only validated
data were used for the determination of precision.
Table E-5 reports the results from the collocated samples
collected in this study for the air TENAX samples. During this
study, a total of 98 valid pairs of duplicate samples were col-
lected. Differences in jj-g/nP were calculated for each sample
pair .when both reported concentrations were above the limit of
quantitation for the pollutant. At the <*=0.01 level of signifi-
cance, none of the mean differences were significantly different
from zero. The standard deviations presented in Table E-5 can be
used to calculate precision estimates for the TENAX field data by
means of the following formula:
Field Results (,ag/m3) ± 1'9* [Std" Dev" from Table E-5
No estimate of precision could be made from collocated sam-
ples for the metals or pesticide analyses because an insufficient
number of duplicate results were obtained to yield meaningful
comparisons. The variability of the estimates of accuracy, how-
ever, can be used to give an approximate estimate of precision
for metals, pesticides, and those volatile organics which also
had too few results from the collocated samples to estimate mea-
surement precision. A percentage interval equal to twice the
standard deviation of the percent difference can be used as an
approximate estimate of data precision for the volatile and met-
als analyses, while twice the percent relative standard deviation
can be used for pesticides and related compounds.
277
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TABLE E-5. RESULTS FROM AIR TENAX DUPLICATE SAMPLES
Compound
Benzene
Carbon tetrachloride
Chlorobenzene
o-Chlorotoluene
p-Chlor otol uene
1 , 2-Dibrome thane
o-Dichlorobenzene
p-Dichlorobenzene
Meant
0.15
-1.05
—
0.60
0.27
—
-3.84
-1.31
Standard
Deviation*
2.99
—
--
0.63
0.45
—
6.48
1.01
Pairs*
52
1
0
3
4
0
9
5
1,1,2,2-Tetrachloro-
ethylene 1.95 10.94 56
Toluene 0.32 10.53 43
MUnits are v-g/m
*A total of 98 valid duplicate pairs of samples were collected.
The number in this column represents the number of pairs where
both results were quantifiable.
ESTIMATES OF DATA ACCURACY
It has been the established practice in air monitoring to
estimate accuracy from independent audits of the measurement pro-
cess (CFR 40, Part 58, Appendix A). An audit of the flow rates
of the field samplers was made during normal sampling periods.
The flow audits were conducted by EPA, and were independent of
the routine flow measurements made by the sampling contractor.
The difference between the contractor flow rate and the EPA de-
termined flow rate can be used to estimate the accuracy of the
sampler flow rate. The results of the flow audits are given in
Table E-6.
In contrast to the standard procedure used to estimate the
accuracy of TENAX measurements, EPA elected to determine accuracy
from the results of the calibration check samples. This was done
because the number of blind audit samples needed to establish ac-
curacy over the analytical range would have approximately equaled
the number of calibration check samples. Doubling the number of
278
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TABLE E-6. RESULTS OF AUDITS OF SAMPLER FLOW RATES
Sampler Type
TENAX
Polyurethane foam
High-volume
Percent
Mean
-1.8
-4.1
-4.3
Difference
Standard
Deviation
2.5
1.8
6.3
Number of
Samplers Audited
31
36
8
quality assessment samples (from 300 to 600) was judged not to be
the most cost-effective means of quantifying accuracy. Because
the calibration check samples and the blind audit samples were
prepared by the same contractor, the results from the check sam-
ples were expected to be similar to the results from the blind
audit samples. Therefore, the percent difference between the
spike value and the analytical result from the calibration check
sample was used to estimate the accuracy of the analyses. The
results of the analyses of all calibration check samples are sum-
marized in Table E-7 for each of the substances that were quanti-
fied.
TABLE E-7. RESULTS FROM THE ANALYSES OF CALIBRATION
CHECK SAMPLES (TENAX ANALYSES)
Percent Difference
Compound
Benzene
Carbon tetra-
chloride
Chlorobenzene
o-Chlorotoluene
1 , 2-Dibromoethane
o-Dichlorobenzene
1,1,2,2-Tetra-
chloroethylene
Toluene
Mean
-2.3
-5.8
-3.9
0.0
-7.5
-1.2
6.9
-2.0
S.D.
28.7
25.2
27.1
25.9
30.3
25.4
25.7
37.1
Number of
Samples
285
307
308
298
309
309
303
276
S.D.: Standard deviation
279
-------
To corroborate the results from the calibration check sam-
ples, blind spike samples were periodically inserted into the
field sample analyses. Results from the blind spike samples
analyses fell within the +_3cr (3 standard deviation) limits estab-
lished from the analyses of the calibration check samples, thus
confirming the estimates obtained from the check samples. The
mean percent differences (Table E-7) were all less than +10 per-
cent. In other ambient air studies, the data are accepted as
reported when biases are documented as less than +10 percent.
To further corroborate the accuracy of the TENAX analyses,
calibration check samples and blind audit samples were analyzed
by an independent laboratory. Only a limited number of samples
(nine) were analyzed by this laboratory during the Love Canal
study resulting in 58 individual analytical results. Ninety-
three percent of these results fell within the +2cr limits estab-
lished from Table E-7, and all the results within the +3cr limits.
Thus, the independent analyses also corroborated the accuracy
estimates.
A further breakdown of the results of the analysis of the
calibration check samples was also performed. The air TENAX cali-
bration check samples were divided into three levels, and the
four separate analytical systems that were used to perform the
analyses. One system, however, was in operation only a few days
and was not included in the statistical analyses. Table E-8 sum-
marizes the analytical results for the air TENAX calibration
check samples by analytical system, and by sample concentration
level (in nanograms per sample). In Table E-8, the mean percent
difference between the reported concentration and the true con-
centration, the standard deviation (S.D.) of this percent dif-
ference, and the number of samples analyzed is presented. Table
E-9 gives the approximate concentrations of the three levels of
calibration check samples used.
Accuracy estimates were made for polyurethane foam samples
through analyses of two blind audit samples that accompanied each
lot of field samples sent to the two analyzing laboratories. Two
of the same samples were also returned to the EPA as blind sam-
ples for analysis by a senior chemist who was not involved with
preparation of the QA samples. The primary purpose of this was
to monitor any losses that might have resulted from the shipping
and handling of the blind samples. The accuracy of analytical
measurements made by the two laboratories was indicated by their
qualitative and quantitative performance on these blind QA sam-
ples. Table E-10 provides a summary of the polyurethane foam
blind check samples results for the two contractor laboratories
and the EPA laboratory.
Analytical accuracy of ICAP metals analyses was also esti-
mated from the results of analyses of audit samples. These sam-
ples were supplied as blind unknowns to the analytical laborato-
ries. The results for ICAP metals accuracy are presented in
280
-------
TABLE E-8.
RESULTS OF ANALYSES OF CALIBRATION CHECK SAMPLES BY
LEVEL AND ANALYTICAL SYSTEMt
Level 1
Compound System Mean S.D.
Benzene
Carbon
tetra-
chloride
Chloro-
benzene
o-Chloro-
toluene
1,2-Dibromo-
ethane
o-Dichloro-
benzene
1,1,2,2-
Tetra-
chloro-
ethylene
Toluene
1
2
3
ALL
1
2
3
ALL
1
2
3
ALL
1
2
3
ALL
1
2
3
ALL
1
2
3
ALL
1
2
3
ALL
1
2
3
ALL
9
-3
-9
-1
-5
12
-16
-6
-4
13
-15
-5
-3
11
-8
-3
0
20
-30
-9
—9
10
-6
-3
4
21
16
13
-9
-15
10
1
.40
.89
.34
.76
.62
.75
.27
.26
.05
.69
.67
.92
.97
.60
.71
.05
.91
.32
.08
.35
.15
.95
.76
.78
.17
.56
.20
.03
.61
.23
.43
.58
40.77
28.79
16.34
30.23
27.60
15.99
16.48
23.00
34.52
21.78
17.14
27.91
26.50
23.31
20.32
24.39
31.94
26.00
13.99
31.59
26.36
19.93
22.67
25.41
27.49
16.35
30.12
27.15
46.40
56.56
26.18
40.72
N
30
16
39
88
30
21
41
96
32
21
41
98
29
21
40
94
30
21
41
96
32
21
41
98
28
21
39
92
15
16
40
73
Level 2
Mean S.D.
8.61
3.79
-7.50
0.24
-14.22
3.43
-3.27
-6.17
1.16
8.36
-10.70
-2.31
2.07
4.71
-3.11
0.75
0.34
3.80
-18.56
-7.49
3.71
9.44
-7.90
-0.10
7.52
6.56
4.94
6.12
6.47
-19.39
-3.40
-3.57
28.72
30.54
21.87
26.76
28.29
17.20
20.07
23.52
27.85
32.14
18.34
26.29
31.59
25.02
22.32
25.83
33.03
26.05
18.69
27.69
29.31
28.45
19.12
25.43
31.73
22.10
20.17
24.39
37.21
43.00
26.18
35.20
N
29
21
47
99
33
22
48
106
32
22
48
105
29
21
48
101
33
22
48
106
32
22
48
105
33
22
47
105
28
22
46
97
Level 3
Mean S.D.
-1.27
8.52
-19.35
-5.21
-14.48
-0.79
-1.08
-4.91
-5.59
8.01
-10.63
-3.46
-4.98
12.23
0.57
2.10
-11.35
11.08
-14.65
-5.92
1.21
11.31
-8.33
0.19
6.73
7.76
-5.64
2.39
-0.73
-0.16
-9.89
-2.95
35.65
26.20
17.25
29.13
33.08
29.45
20.93
28.78
29.55
32.30
15.79
27. 17
25.88
33.04
22.14
27.13
33.10
35.80
21.66
31.82
28.95
28.24
15.20
25.50
28.67
28.29
16.36
24.88
43.95
43.62
17.74
36.36
N
33
26
37
98
33
30
39
105
34
29
39
105
32
29
39
103
35
30
39
107
34
30
39
106
34
30
39
106
34
30
39
106
"Units for mean and standard deviation (S.D.) are percent difference.
281
-------
TABLE E-9.
APPROXIMATE CONCENTRATIONS OF CALIBRATION
CHECK SAMPLES
Compound
Level 1
Benzene
Carbon tetrachloride
Chlorobenzene
o-Chlorotoluene
1 , 2-Dibromoethane
o-Dichlorobenzene
1,1,2, 2-Tetrachloro-
ethylene
Toluene
Level 2
11
7
10
9
8
9
12
11
18
12
17
18
13
18
19
19
TABLE E-10. SUMMARY OF RESULTS FOR POLYURETHANE
Check
Compound
1,2,3,4-Tetra- Level
chlorobenzene Average
SD
% RSD
N
Pentachloro- Level
benzene Average
SD
% RSD
N
Hexachloro- Level
benzene Average
SD
% RSD
N
T-BHC (Lindane) Level
Average
SD
% RSD
N
2,4,5-Tri- Level
chlorophenol Average
SD
% RSD
N
1
1,000 ng
74.4
+14.1
18.9%
11
400 ng
77.3
+ 9.9
12.9%
11
600 ng
99.2
+22.9
23.1%
11
100 ng
69.9
+23.0
32.9%
11
300 ng
75.1
+35.2
46.9%
12
2
1,500 ng
78.
+12.
15.
11
200
86.
+17.
20.
11
300
116.
+42.
36.
12
150
77.
+18.
23.
11
3
3
7%
ng
3
7
5%
ng
2
8
9%
ng
5
2
5%
150 ng
89.
+53.
60.
11
6
8
1%
3
750
77.
+25.
32.
10
100
83.
+26.
32.
10
150
104.
+47.
45.
10
75
67.
+48.
71.
10
75
90.
+57.
63.
10
Level
29
20
26
27
19
27
31
28
FOAM CHECK
3
SAMPLES'
Sample Number
ng
6
6
9%
4
5
3,000 ng
64.
+16.
26.
8
3
9
2%
ng 1,000 ng
3
7
1%
ng
2
5
6%
ng
9
8
9%
ng
4
5
6%
69.
+27.
38.
9
120
91.
+31.
34.
8
200
68.
+22.
33.
9
100
68.
+38.
55.
9
7
0
8%
ng
1
2
3%
ng
6
7
2%
ng 1
4
0
5%
750
81
+ 15
19
16
500
85
+ 18
"21
16
200
94
+27
29
16
250
79
+20
"25
16
,000
77
+37
48
17
ng
.8
.8
.3%
ng
.1
.2
.3%
ng
.9
.8
.2%
ng
.7
.0
.1%
ng
.1
.1
.1%
6
900
87
+21
~24
12
400
86
+19
22
11
200
84
+22
27
10
250
82
+22
-27
11
200
86
+16
19
10
ng
.5
.5
.5%
ng
.4
.6
.7%
ng
.3
.7
.0%
ng
.1
.3
.2%
ng .
.2
.4
,1%
Percent recovery + SD, with percent relative standard deviation and number
of samples
282
-------
Table E-ll. Analytical accuracy for NAA metals analyses was
estimated from the results of NBS Standard Reference Materials.
These results are presented in Table E-12.
Mean percent differences for all metals analyses were less
than jf5 percent, except for zinc, which was -11 percent. No
changes to the metals data were made based on these results.
These results were judged consistent with the results obtained by
EMSL-RTP, both prior and subsequent to the analysis of Love Canal
samples.
TABLE E-ll.
RESULTS FROM THE ANALYSIS OF
BLIND AUDIT SAMPLES BY ICAP
Element
Lead
Nickel
Zinc
Percent
Mean
-0.1
-1.9
-11.2
Difference
S.D.
3.7
4.3
5.5
Number of
Samples
6
6
6
S.D.: Standard deviation
TABLE E-12. RESULTS FROM THE ANALYSIS OF NATIONAL BUREAU OF
STANDARDS STANDARD REFERENCE MATERIALS BY NAA
SRM 1648
Percent Difference
Element
Arsenic
Cobalt
Chromium
Mean
4.7
1.4
-4.5
S.D.
10.1
4.4
4.3
SRM 1632
Percent Difference
Mean
-3.5
4.9
0.0
S.D.
7.9
2.9
3.1
Number of
Samples
12
12
12
S.D.: Standard deviation
Note: For each SRM, 12 separate analyses were performed.
SUMMARY OF MAJOR ACTIONS TAKEN AS A RESULT OF THE GCA CORPORATION
QUALITY ASSURANCE FUNTIONS
While most actions taken by EPA as a result of the quality
assurance program occurred after analyses had been completed, the
GCA Corporation quality assurance program was operative during
the on-going measurement processes. One indication of the effec-
tiveness of the GCA Corporation QA program was the fact that very
few samples had to be invalidated retrospectively by EPA during
283
-------
its review of the data. To a great extent, the low number of in-
validated samples were due to the adherence of the sampling and
analytical subcontractors to the required quality assurance pro-
cedures. In addition, the GCA Corporation's management of the
monitoring efforts, timely identification of potential problems,
and initiating corrective actions before these problems became
major resulted in analytical laboratories operating in control.
Some examples of the GCA Corporation quality assurance activ-
ities that eliminated minor problems before they adversely af-
fected the data are as follows:
1. By reviewing the results of the calibration check samples
(TENAX analyses) as they were reported, the GCA Corpora-
tion noticed that variability in one laboratory was ap-
proaching unacceptable limits. A site investigation by the
GCA Corporation of the laboratory in question uncovered a
minor leak in the injection system to their GC/MS. The
leak was corrected, and variability of results on the cal-
ibration check samples decreased. No data needed to be
invalidated because the problem was corrected while it was
still minor.
2. The GCA Corporation monitored the TENAX tube clean-up
dates at their Love Canal sample bank operation, and re-
moved blank tubes which, in their estimation, could not be
used to collect a sample and be analyzed within the pre-
scribed 30-day time limit established at the start of the
monitoring program. By this activity, the 30-day limit
was adhered to throughout the study.
3. Once the TENAX collecting media was cleaned, a number of
tubes from each batch were analyzed for background before
the tubes were sent to the field. As a result, one com-
plete batch of TENAX was rejected and removed from the
study because of unacceptably high background analytical
results.
Additional examples of the GCA Corporation on-going quality
assurance activities are described in the Love Canal Monitoring
Program, GCA QA/QC Summary Report.
284
-------
REFERENCES
1. Pellizzari, 1, D. Development of Analytical Techniques for
Measuring Ambient Atmospheric Carcinogenic Vapors. Publica-
tion No. EPA-600/2-75-075, Contract No. 68-02-1228. Novem-
ber 1975. 187 pp.
2. . The Measurement of Carcinogenic Vapors in
Ambient Atmospheres. Publication No. EPA-600/7-77-055, Con-
tract No. 68-02-1228. June 1977. 288 pp.
3. — • . Evaluation of the Basic GC/MS Computer Analy-
sis Technique for Pollutant Analysis. Final Report, EPA
Contract No. 68-02-2998.
4. Pellizzari, E. D. , and L. W. Little. Collection and Analy-
sis of Purgeable Organics Emitted from Treatment Plants.
Final Report, EPA Contract No. 68-03-2681. 216 pp.
5. Pellizzari, E. D. Analysis of Organic Air Pollutants by Gas
Chromatography and Mass Spectroscopy. EPA-600/2-77-100.
June 1977. 114 pp.
6. . Analysis of Organic Air Pollutants by Gas
Chromatography and Mass Spectroscopy. EPA-600/2-79-057.
March 1979. 243 pp.
7. , Ambient Air Carcinogenic Vapors Improved
Sampling and Analytical Techniques and Field Studies. EPA-
600/2-79-081. May 1979. 340 pp.
8. Lewis, R. G», A. R. Brown and M. D. Jackson. Evaluation of
Polyurethane Foam for Sampling of Pesticides, Polychlorina-
ted Biphenyls, and Polychlorinated Napthalenes in Ambient
Air. Anal. Chem. 49. 1977. 1668-1672.
9. Lewis, R. G. "Sampling and Analysis of Airborne Pesti-
cides", in Air Pollution from Pesticides and Agricultural
Processes. R. E. Lee, Jr. (Ed.), CRC Press. 1976. pp.
52-94.
10. Lewis, R, G. , K. E. MacLeod, and M. D. Jackson. Sampling
Methodologies for Airborne Pesticides and Polychlorinated
Biphenyl. Paper No. 65, Chemical Congress, ACS-Chemical
Society of Japan, Honolulu, Hawaii, April 2-6, 1979.
11. Manual of Analytical Methods for the Analysis of Pesticides
in Humans and Environmental Samples, Section 8. U.S. Envi-
ronmental Protection Agency, Health Effects Research Labora-
tory, Research Triangle Park, North Carolina 27711, EPA-
600/8-80-038. June 1980.
285
-------
12. MacLeod, K. E. Sources of Emissions of PCBs into the Ambi-
ent Atmosphere and Indoor Air. U.S. Environmental Protec-
tion Agency, Health Effects Research Laboratory, Research
Triangle Park, North Carolina 27711, EPA-600/4-78-022.
March 1979.
13. Bidleman, T. F., J, R. Matthews, C. E. Olney and C. P. Rice.
Separation of PCBs, Chlordane, and p_p_'-DDT from Toxaphene by
Silicic Acid Column Chromatography. J. Assoc, Off. Anal.
Chem. , 61:820-828.
14. Lewis, R. G., M. D. Jackson and K. E. MacLeod. Protocol for
the Assessment of Human Exposure to Airborne Pesticides.
U.S. Environmental Protection Agency, Health Effects Re-
search Laboratory, Research Triangle Park, North Carolina,
EPA-600/2-80-180. 1980.
286
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APPENDIX F
REPORT ON THE AUDIT OF GAS CHROMATOGRAPHY/
MASS SPECTRQMETRY DATA PROVIDED BY
LOVE CANAL PROJECT ANALYTICAL LABORATORIES
INTRODUCTION
This report provides the results of an audit of raw gas
chromatography/mass spectrometry (GC/MS) data archived on magnet-
ic tape and provided by the Love Canal project analytical labo-
ratories. It is emphasized that the audit was not applied to the
complete analyses of samples by the contract laboratories, but
only to the interpretation of raw GC/MS data as provided on mag-
netic tape .
The audit was accomplished by three EPA laboratories using
Protocol for Auditing Gas Chromatography/Mass Spectrometry Data
Provided by Love Canal Project Analytical Laboratories, revision
1.01 by W. L. Budde, E. H. Kerns, and J. W. Eichelberger , dated
July 2, 1981. The participating EPA laboratories were the Envi-
ronmental Monitoring and Support Laboratory, Cincinnati (EMSL-
Cin) , the Environmental Monitoring Systems Laboratory, Las Vegas
(EMSL-LV) , and the Environmental Research Laboratory, Athens
(ERL-Athens) .
SCORING SYSTEM — TARGET COMPOUNDS
In order to provide a quantitative measure of the performance
of the laboratories, a scoring system was developed. This scor-
ing system is based on two indices, the positive agreement index
(PAI) and the negative agreement index (NAI), which are defined
as follows;
TP
PAI = - i=- - xlOO%
287
-------
where:
TP = the number of corapounas on the method target
compound list that were found by the analytical
laboratory and confirmed to be present in the
magnetic tape record of the analysis by the
audit laboratory.
T = the total number of compounds on the method
target compound list that were found by the
analytical laboratory plus any additional tar-
get compounds that were found by the audit lab-
oratory.
N = the number of method target compounds.
The PAI is a statement of the percentage of positive occurrences
the two laboratories agreed upon; and, the NAI is a statement of
how well the two laboratories agreed on what target compounds
were not present above the method detection limit. The audit
data used to compute the PAI and NAI values for the samples
audited are shown in Tables F-l and P-2 (laboratory abbreviations
are explained in Table 4 of the text). For Method 624, the value
of N was 39; for Method 625, the value of N was 68. The summary
PAI and NAI values shown in Tables F-l and F-2 were computed for
each laboratory from the totals shown in the tables, and there-
fore represent the weighted means. The weighted NAI values were
computed using a value of N weighted by the number of samples of
each type (Method 624 or 625).
For most of the possible boundary conditions, the minimum and
maximum values of the PAI and NAI indices are 0 and 100 percent.
However, if no compounds are in the sample and both laboratories
are in perfect agreement on this condition, the PAI is undefined,
and the index has no meaning. If every single target analyte is
present and both laboratories are in perfect agreement on this
condition, the NAI is undefined and the index has no meaning.
To assist in interpreting the PAI and NAI scores, it was de-
sirable to establish a reference point for performance. The
EMSL-Cincinnati had acted as a referee quality assurance labora-
tory during the project, and analyzed 5 percent of the water sam-
ples and 3 percent of the soil and sediment samples (Tables F-3
and F-4). Data from three of the samples analyzed by EMSL-Cin-
cinnati were audited by ERL-Athens to establish the level of
agreement between two highly experienced laboratories that were
also involved in the development of the methods and motivated to
generate high quality scientific work (and work that was rela-
tively free from the fixed price financial constraints that ex-
isted at the contract laboratories and which may have impinged on
performance) . The weighted mean PAI for these 3 samples was 71
percent and the weighted mean NAI was 94 percent. On this basis,
288
-------
TABLE F-l.
SUMMARY OF EMSL-CINCINNATI AUDIT
OF LOVE CANAL GC/MS WATER SAMPLES
Lab.
ACEE
PJBL
TRWW
CMTL
Method
624
624
624
624
624
624
624
624
624
624
625
625
625
625
624
624
625
625
625
625
624
624
624
624
624
624
624
625
625
625
625
Sample No
W20877
W20922
W21732
W25290
W25506
W25511
W25628
W25629
W25654
W25656
W20872
W21733
W25507
W25625
W20796
W20825
W20349
W20808
W20820
W20856
W21976
W22008
W22009
W22026
W21644
W21663
W21773
W21774
W21645
W21818
W25123
T
3
1
2
6
7
4
4
5
3
10
1
16
0
0
62
15
3
9
24
3
0
54
10
8
15
15
48
2
0
0
0
0
0
0
2
TP
1
0
1
5
5
2
2
5
3
10
1
15
0
0
50
9
3
7
11
3
0
33
8
5
9
11
33
0
0
0
0
0
0
0
0
PAI
33
0
50
83
71
50
50
100
100
100
100
94
undefined
undefined
81
60
100
78
46
100
undefined
61
80
63
60
73
69
0
undefined
undefined
undefined
undefined
undefined
undefined
0
NAI
95
97
97
97
94
95
95
100
100
100
100
98
100
100
98
80
100
97
77
100
100
93
94
91
80
86
88
95
100
100
100
100
100
100
99
(continued)
289
-------
TABLE F-l (continued)
Lab.
GSRI
EMSL-
Cin
Method
625
625
625
625
625
625
625
625t
6251"
Sample No.
W21516
W21526
W21537
W25421
W25432
W25525
W25564
W21725
W25199
T
1
6
0
1
0
7
0
15
12
3
15
TP
0
6
0
1
0
6
0
13
9
2
11
PAI
0
100
undefined
100
undefined
86
undefined
87
75
67
73
NAI
99
100
100
100
100
98
100
100
95
98
97
^Audited by ERL-Athens
TABLE F-2.
SUMMARY OP THE EMSL-LAS VEGAS AND ERL-ATHENS AUDIT
OF LOVE CANAL SOIL AND SEDIMENT SAMPLES
Lab . Method
ACEE 6241"
624
624
624
624
624
624
625
625
625
PJBL 624
624
624
624
Sample No. T
S50158
S40085
S40121
S40576
S40586
S50150
S50296
S40087
S40209
S45206
S45526
S45527
S50257
S50262
(
0
4
1
4
1
5
4
0
0
13
32
5
6
7
6
24
continued
TP
0
3
1
2
0
2
2
0
0
10
20
4
3
4
2
13
)
PAI
undefined
75
100
50
0
40
50
undefined
undefined
77
63
80
50
57
33
54
NAI
100
97
100
95
97
92
95
100
100
95
97
97
92
91
89
92
^Audited by ERL-Athens
290
-------
TABLE F-2 (continued)
Lab , Method
CMTL 624
624
624
624
624
624
625
625
625
GRSI 625
625
625
625
625
624
624
624
624
624
624
SWRI 625
625
625
625
625
625
625
EMSL-Cin 62 5*
Sample No.
S45018
S45027
S45219
S45398
S50025
S50031
S45054
S45119
S50047
S40330
S40332
S40463
S40464
S40491
S40414
S40417
S40425
S40426
S50238
S50380
S40058
S40178
(N25W15)
S40178
(KF25W16)
S40796
S40888
S40908
S50330
S50068
T
2
2
2
3
9
5
0
10
18
51
0
0
0
6
2
0
2
1
0
3
6
20
11
19
21
13
6
15
19
104
20
TP
0
0
1
0
7
2
0
5
7
22
0
0
0
3
0
0
2
1
0
3
4
13
5
10
9
10
3
9
17
63
14
PAI
0
0
50
0
78
40
undefined
50
39
43
undefined
undefined
undefined
50
0
undefined
100
100
undefined
100
67
65
45
53
43
77
50
60
89
61
70
NAI
95
95
97
92
94
92
100
92
82
93
100
100
100
95
97
100
100
100
100
100
94
99
90
84
80
95
95
90
96
90
89
'''Audited by ERL-Athens
291
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TABLE F-3. SUMMARY OF THE LOVE CANAL WATER DATA AUDIT
Samples
Analytical Reported*
Laboratory (624 + 625)
ACEE
CMTL
EMSL-Cin
ERGO
GSRI
ERL-Ada
PJBL
TRWW
Totals
214
149
38
1
159
8
127
69
765
Percent Percent of Subcontractor
of Number Audited by Lab's Total Audited by
i Total EMSL-Cin ERL-Athens EMSL-Cin ERL-Athens
28 14 — 6.5
19 7 — 4.7
5 — 2 — 5.3
o
21 7 -- 4.4
"1 •*.,•» mm. — — :• muii
17 6 — 4.7
9 4 — 5.8
100 38(5%) 2(0.26%)
'In validated data base
TABLE F-4. SUMMARY OF THE LOVE CANAL SOIL AND SEDIMENT AUDIT
Samples
Analytical Reported*
Laboratory (624 + 625)
ACEE
CMTL
EMSL-Cin
GSRI
PJBL
SWRI
Totals
150
195
24
141
18
174
702
Percent
of
Total
21
28
3
20
3
25
100
Percent of Subcontractor
Number Audited by Lab's Total Audited by
ERL-Athens EMSL-LV ERL-Athens EMSL-LV
1 9 0.7
9
1 4.2
6 5 4.3
4
7
8(1.1%) 34(4.8%)
6.0
4.6
3.5
22.0
4.0
validated data base
292
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it was judged not reasonable to expect a contract analytical lab-
oratory to "have any better agreement with an EPA audit laboratory
than the two expert EPA laboratories had with each other. Conse-
quently, it was assumed that reasonable, perhaps state-of-the-
art, performance would be a PAI of 71 percent or better, and a
NAI of 94 percent or better.
Throughout the audit, the results reported in the validated
data base were compared with the audit laboratory's interpreta-
tion of the magnetic tape files. In some cases files from method
blanks were available, and background from laboratory contami-
nants was subtracted before the scores were computed. In other
cases, clearly corresponding files from method blanks could not
be located and, while the analytical laboratory was given the
benefit of the doubt on common laboratory contaminants, some
additional uncertainty exists in the scores that needs to be con-
sidered when interpreting them. Therefore, a reasonable range of
uncertainty may be +10 percent for PAI and a reasonable accept-
ance range for PAI scores would be 61 to 81 percent. Missing
method blank files and other uncertainties were judged to have
much less impact on NAI scores and a reasonable acceptance range
may be +5 percent or a NAI score of 89 to 99 percent.
LABORATORY SCORES—TARGET COMPOUNDS
Tables F-3 and P-4 show the number of samples in the val-
idated data base analyzed by each laboratory, the percent of the
totals, the number audited, and the percent of each laboratory's
total that was audited. Overall, 5.26 percent of the water sam-
ples and 5.9 percent of the soil and sediment samples were ran-
domly selected from the validated data base and subsequently
audited. At the beginning of the program, the target audit per-
centage was 5 percent, and deviations from this were caused by a
number of factors including? (1) incorrect early estimates of
the number of samples analyzed by each laboratory? (2) the fail-
ure to achieve distribution of all the magnetic tapes by the
audit deadline; and (3) inability of the audit laboratories to
read some tapes because of technical difficulties. In general,
the intensity of the audit is believed to be acceptable and re-
presentative of the overall performance of contractor laborato-
ries, that is, the conclusions would not change if double or
triple the number of samples were audited. However, there were
several exceptions where a reliable audit of contractor labora-
tory performance was not obtained. The laboratory CMTL was very
slow in submitting data, and six of the seven water samples exam-
ined had no target compounds above the minimum detection limit.
This resulted in nearly all audited samples having undefined PAI
scores and the resulting audit was judged indeterminate. In sim-
ilar fashion, the laboratory GSRI had three undefined water PAI
scores which reduced the valid audited percentage to a very low
2.5 percent. On the other hand, the GSRI laboratory had five
undefined PAI scores for soil and sediment samples, but the re-
maining six accounted for a reasonable 4. 2 percent of the total
soil and sediment samples analyzed by this laboratory.
293
-------
Examination of Table F-l reveals that all the weighted PAI
means, except that of CMTL which was discussed previously, fall
into the acceptance range of 61 to 81 percent or higher. Similar-
ly, the NAI scores are all in the range of 89 to 99 percent ex-
cept TRWW, which had an 88 percent. Only a few individual scores
fell outside these reasonable acceptance ranges.
Among the laboratories analyzing soil and sediment samples,
two laboratories (PJBL and CMTL) had below acceptable weighted
mean PAI scores; all laboratories had weighted mean NAI scores in
the acceptable range. The PJBL laboratory analyzed only 18, or 3
percent, of the total soil and sediment samples and was removed
from the contract work early in the program for quality assurance
reasons. The identification of potential QC problems associated
with the performance of CMTL in soil and sediment analyses was
substantially hampered by the late delivery of data to the prime
contractor and EPA.
DISCUSSION—TARGET COMPOUNDS
The raw archived GC/MS data was studied carefully to assess
those factors contributing to the generally less than perfect
agreement on positive occurrences between contractor and EPA
audit laboratories and between EPA laboratories. In general, it
was found that the contributing factors reduced to differences in
computer algorithms used by various laboratories to automatically
detect peaks in total or partial ion chromatograms, and to dis-
tinguish real signals from chemical and other noise. Another
major reason was found to be differences in judgment and identi-
fication criteria employed by various equipment operators and
data interpreters. Although EPA methods do provide compound
identification criteria, interpretations were found to differ at
times, especially where there was little or no direct communica-
tion among interpreters at many sites. Different interpretations
were especially noticed at concentrations below 30 parts per bil-
lion, which is the region of the method detection limit for many
compounds. It was observed that some data interpreters were
willing to accept mass spectra with some chemical noise (back-
ground) as valid proof for an identification, while other inter-
preters required relatively clean spectra before accepting an
identification as correct.
A group of 18 water samples that contained 52 discrepancies
in the findings of the analytical and audit laboratories was ex-
amined carefully to determine the effect of concentration levels.
Of the 52 discrepancies, 49 occurred at concentrations below 30
micrograms per liter, which is well into the region of detection/
quantitation limits for many of the laboratories. Of the 49 oc-
currences, 22 were reported as "trace" amounts. The remaining 3
discrepancies, which occurred above 30 parts per billion, may
possibly be accounted for by missing method blanks. As was
pointed out previously, clearly corresponding data files from
294
-------
method blanks could not always be located for the audit. Conse-
quently, in some samples, compounds were found by the audit lab-
oratory that were not reported by the analytical laboratory, and
some of these may have been present in the method blank, which
caused the analytical laboratory to delete the compound from the
report. Furthermore, the conclusions of the study were based on
levels of contamination that were orders of magnitude higher than
the parts per billion levels that seemed to dominate the discrep-
ancies between the analytical and audit laboratories. Therefore,
the discrepancies in findings have little or no affect on the
overall conclusions of the study.
NON-TARGET COMPOUNDS
The analytical laboratories were required by the terms of
their subcontracts to attempt to identify up to 20 of the most
abundant compounds in each sample that were not on the target
compound list (non-target compounds). Table F-5 summarizes the
results of the audit of this effort. In this table the infor-
mation from water, soil, and sediment samples analyzed by both
GC/MS methods was consolidated.
TABLE F-5. SUMMARY OF NON-TARGET COMPOUND AUDIT
Number of samples audited 80
for non-targeted compounds
(39 water, 41 soil and sediment)
Number of samples in which 58(72.5%)
the analytical laboratories
and the audit laboratories
agreed that none were present
Total number of compounds r
identified by the analytical
laboratories in the 22
remaining samples
Total number of compounds 84
identified by the audit
laboratories in the 22
remaining samples
^Does not include 19 identifications reported by EMSL-Cinein-
nati as an analytical laboratory in 2 samples
Does not include 16 identifications reported by ERL-Athens as
an audit laboratory for EMSL-Cincinnati as the analytical
laboratory in 2 samples
295
-------
hs can be seen from the results presented in Table F-5, the
audit and analytical laboratories agreed that no non-target com-
pounds were present in nearly three-fourths of the samples re-
viewed. In most of the 22 samples containing non-target com-
pounds the audit laboratory reported finding 1 or 2 compounds
while the analytical laboratory reported none. There were 5
samples audited where 6 to 20 compounds were reported by the
audit laboratory but none were reported by the analytical lab-
oratory (CMTL and SWRI).
The results of the non-target compounds audit revealed that
the estimated concentration levels of most omitted compounds was
in the vicinity of the method limits of detection and quantita-
tion. Furthermore, it was found that in those relatively few
samples in which a discrepancy occurred in reporting non-target
compounds, the audit and analytical laboratories agreed that the
samples were already heavily contaminated with targeted com-
pounds. Consequently, the results of the audit of non-target
compounds was judged to not affect the general findings of the
project.
CONCLUSION
Considering the extremely rapid start-up and completion of
this project, which allowed very little time to develop the ca-
pabilities of the contract analytical laboratories, and the rapid
response times required of the laboratories, the overall perform-
ance of contract laboratories was judged to be acceptable. In
general, the overall findings of the project would not have been
materially affected even if there had been perfect agreement be-
tween the analytical laboratories and the audit laboratories.
This is because the great majority of discrepancies in the find-
ings of the analytical and audit laboratories involved substances
occurring at concentration levels in the vicinity of the method
limits of detection and quantitation, and these discrepancies
were nearly always restricted to samples that were correctly
identified as being heavily contaminated with targeted compounds.
The major conclusions of the monitoring study, however, were
based on findings of environmental contamination at orders of
magnitude higher concentration levels than the estimated con-
centrations levels comprising nearly all discrepancies.
296
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