6EFA
United States
Environmental Protection
Agency
Off ice of
Solid Waste and
Emergency Response
9285.9-178
EPA/540/R-96/035
PB96-963248
December 1996
Superfund
Sampling for Hazardous
Materials (165.9)
Student Manual
-------
e re
9285.9-17B
EPA54OIR-96/035
PB 9 6-9 63 248
FOREWORD
This manual is for reference use of students enrolled in scheduled training courses of the U.S.
Environmental Protection Agency (EPA). While it will be useful to anyone who needs information
on the subjects cpvered, it will have its greatest value as an adjunct to classroom presentations
involving discussions among the students and the instructional staff.
Thi 1 nanual has been developed to provide the best available current information; however,
individual instructors may provide additional material to cover special aspects of their presentations.
Because of the limited availability of the manual, it should not be cited in bibliographies or other
publications.
References to products and manufacturers are for illustration only; they do not imply endorsement
by EPA.
Constructive suggestions for improvement of the content and format of the Sampling for Hazardous
Materials (165.9) manual are welcome.
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SAMPLING FOR HAZARDOUS MATERIALS (165.9)
3 Days
This course provides individuals who have little or no sampling experience with practical information for
effectively sampling hazardous materials at Superfund sites. The course focuses on sampling plan
development, types of equipment suitable for hazardous materials sampling, and procedures for safely
collecting samples. It is intended for personnel responsible for inspections, investigations, and remedial
actions at Superfund sites. Air sampling is specifically addressed in Air Monitoring for Hazardous
Materials (165.4) and is not discussed in this course.
The course is designed to be consistent with the EPA protocol and guidance documents entitled A
Compendium of Superfund Field Operations Methods and Data Quality Objectives for Remedial Response
Activities.
Topics that are discussed include sample plan development; procedures for sampling containerized
materials, surface water/lagoons, sediments/sludges, and soil; soil gas sampling; field screening
techniques; documentation; and quality assurance.
Instructional methods include lectures, group discussions, demonstrations, classroom exercises, and
outdoor field exercises, emphazing the hands-on use of multimedia sampling equipment.
After completing the course, participants will be able to:
• Select the appropriate field screening method for a given contaminant and geologic
environment.
• Select the appropriate sampling container and sample preservation method based on the
sample media and analysis required.
• Select the appropriate sampling implements and methods for sampling various
containerized wastes.
• Select the appropriate tools and methods for sampling surface water and sediments.
• Describe the basic methods of soil sampling in the unsaturated zone.
• Demonstrate the proper method for obtaining a groundwater sample from a monitoring
well.
• Complete the required documentation, including chain of custody and sample labels, for
shipment of environmental samples to an analytical laboratory.
• Complete fundamental tasks in a sampling event from initial site investigation through
field data collection.
Ill
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CONTENTS
Section 1 Orientation and Introduction
Section 2 Sample Plan Development
• Quality Assurance Sampling Plan for Emergency Response
• Appendix II of Guidance for Data Useability in Risk Assessment
(Part A)
Section 3 Field Screening
• Environmental Photographic Interpretation Center (EPIC)
Section 4 Documentation
Section 5 Field Screening Exercise
Section 6 Containerized Material Sampling
• Hazard Categorization
Section 7 Groundwater Sampling
Section 8 Surface Water and Sediment Sampling
Section 9 Soil Sampling
Section 10 Field Exercise
Problem Session: Sample Plan Development Exercise
V
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ACRONYMS AND ABBREVIATIONS
AMD Advanced Monitoring Systems Division
AMS air monitoring system
API American Petroleum Institute
ARAR applicable or relevant and appropriate requirements
ASCS Agricultural Stabilization and Conservation Service
ASTM American Society for Testing and Materials
BNA base/neutral and acid extractables
BTEX benzene, toluene, ethylbenzene, and xylenes
CBI confidential business information
CDP common depth point
CERCLA Comprehensive Environmental Response, Compensation and Liability Act
CFR Code of Federal Regulations
CGI combustible gas indicator
CLP Contract Laboratory Program
COC chain of custody
COE U.S. Army Corps of Engineers
COLIWASA composite liquid waste sampler
CRDL contract-required detection limit
CRQL contract-required quantitation limit
CWA Clean Water Act
DCO document control officer
DL detection limit
DOT U.S. Department of Transportation
DQO data quality objectives
EAU evidence audit unit
Eh oxidation-reduction potential (redox potential)
EM electromagnetic
EMSL-LV Environmental Monitoring and Support Laboratory-Las Vegas
EPA U.S. Environmental Protection Agency
EPIC Environmental Photographic Interpretation Center
ESD Environmental Services Division (EPA)
FJD flame ionization detector
FIPS federal information processing standards
FIT field investigation team
FS feasibility study
FSP field sampling plan
FTS federal telephone system
v ii
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Acronyms and Abbreviations (continued)
GC gas chromatograph or gas chromatography
GC/MS gas chromatography/mass spectroscopy
GIS geographic information system
GPR ground-penetrating radar
HAZCAT hazard categorization
HRS hazard ranking system
HSL hazardous substance list
IATA International Air Transport Association
DL instrument detection limit
LEL lower explosive limit
MDL method detection limit
NAPL nonaqueous phase liquid
NAPP National Aerial Photography Program
ND nondetect
NEIC National Enforcement Investigation Center
NHAP national high altitude photography
NMO normal movement
n.o.s. not otherwise specified
NPDES National Pollutant Discharge Elimination System
NFL National Priorities List
NTIS National Technical Information Service
OD outside diameter
OSHA Occupational Safety and Health Administration
OSWER Office of Solid Waste and Emergency Response
OVA organic vapor analyzer
PAN polycyclic aromatic hydrocarbon
PARCC precision, accuracy, representativeness, completeness, arid comparability
PCB polychiorinated biphenyl
PE performance evaluation
PB) photoionization detector
POTW publicly owned treatment works
PPM parts per million
PPB parts per billion
PRP potentially responsible party
PTFE polytetrafluoroethylene
PVC polyvinyl chloride
vu’
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Acronyms and Abbreviations (continued)
QAO quality assurance officer
QAP quality assurance plan
QAPjP quality assurance project plan
QA/QC quality assurance/quality control
RA remedial action
RAS routine analytical services
RCRA Resource Conservation and Recovery Act
RD remedial design
RDCO regional document control officer
REAC Response Engineering and Analytical Contract
RI remedial investigation
ROD record of decision
RPM remedial project manager
RSCC Regional Sample Control Center
SAP sampling and analysis plan
SARA Superfund Amendments and Reauthorization Act
SAS special analytical services
SCS Soil Conservation Service
SDWA Safe Drinking Water Act
SIC standard industrial classification
SM site manager
SMO Sample Management Office
SOP standard operating procedure
SOW statement of work
SW-846 Test Methods for Evaluating Solid Waste (SW-846) (EPA document)
TAL Target Analyte List
TCDD tetrochlorodibenzo-p-dioxin
TCL Target Compound List
TDS total dissolved solids
TIC tentatively identified compounds
TOC total organic carbon
TOX total organic halogens
TR traffic report
TSCA Toxic Substances Control Act
USGS U.S. Geological Survey
VOA volatile organic analysis
VOC volatile organic compound
ix
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Section 1
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Sampling for Hazardous Materials
(165.9)
Orientation and Introduction
Student Guide
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SAMPLING FOR
HAZARDOUS MATERIALS
(165.9)
Presented by:
Halliburton NUS Corporation
EPA Contract No. 68-C2-0121
Orientation and Introduction
Agenda:
• Environmental Response Training Program (ERTP) overview
• Synopsis of ERTP courses
• Course layout and agenda
• Course materials
• Facility information
Sampling fo( Hazardoua Materials os /ge
Onen on and InUOdUCIJOri page 2
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Notes:
0 1/ 06
Samp1.n for Hazardous f 4athirsIs page 3
Or,entaton and Irtoducdon
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ERTP OVERVIEW
Comprehensive Environmental Response, Compensation
and Liability Act of 1980
Superfund Amendments and Reauthorization Act of 1986
(SARA)
_ . _ . .. _ .:
U.S. Environmental Protection Agency
(EPA)
::: 3::. .:. c: z:. :
Environmental Response Training Program
(ERTP)
S•S . .... ‘ ‘. “ .‘S” ’ ‘ ‘
ERTP Overview
In 1980, the U.S Congress passed the Comprehensive Environmental Response, Compensation and
Liability Act (CERCLA), also known as Superfiind. In 1986, the Superfund Amendments and
Reauthorization Act (SARA) was passed. This act amended CERCLA CERCLA provides for liability,
compensation, cleanup, and emergency response for hazardous substances released into the environment
and for the cleanup of inactive waste disposal sites. The U S. Environmental Protection Agency (EPA)
allocated a portion of Superfimd money to training. EPA’s Environmental Response Team (ERT)
developed the Environmental Response Training Program (ERTP) in response to the training needs of
individuals involved in Superfund activities
Sarrpl.ng ?o Hazardou. Mat.c ,. . 01 108
Orient Uon nd InUoduct ,on pa9e 4
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Notes:
0 1 1 9 8 -
Sampling icr Hazardous Matflhs 5
Onentabon and Introducton
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U.S. Environmental Protection Agency
(EPA)
Office of Solid Waste and Emergency Response
(OSWER)
Environmental Response Team
(ERT)
Environmental Response Training Program
(ERTP)
ERTP Overview (cont.)
ERTP is administered by ERT, which is part of the Office of Solid Waste and Emergency Response
(OSWER) ERT offices and training facilities are located in Cincinnati, Ohio, and Edison, New Jersey
ERT has contracted the development of ERTP courses to Halliburton NUS Corporation (EPA Contract
No 68-C2-0121) ERTP provides education and training for environmental employees at the federal,
state, and local levels in all regions of the United States Training courses cover areas such as basic
health arid safety and more specialized topics such as air sampling and treatment technologies.
S2mphng Voi Hazardous Mateosls 01196
Onentatjoii and Introduction psgn 6
ERTP OVERVIEW (cont.)
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Notes:
01190
Sampling tot’ HUafdQu$ M.± naIi page 7
Onantobon and nbcdu cn
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Continuing Education Units (CEUs)
2.00 CEUs: 100% attendance at this course
> 70% on the exam
Types of Credit Available
arrp! fl9 fw Hdzdrdous Matenals
( r, ’r atjon and I,dToductlon
01 /98
page 8
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Notes:
Sampling ton Hazsrdou. Matetlats 01190
On.ntauon and lntmducbon pago 9
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ERTP Courses
Health and Safety Courses
• Hazardous Materials Incident Response Operations (165.5)
• Safety and Health Decision-Making for Managers (165.8)
• Emergency Response to Hazardous Material Incidents (165 15)
Technical Courses
• Treatment Technologies for Superfund (165.3)
• Air Monitoring for Hazardous Materials (165.4)
• Risk Assessment Guidance for Superfund (165.6)
• Introduction to Groundwater Investigations (165.7)
• Sampling for Hazardous Materials (165.9)
• Radiation Safety at Superfund Sites (165.11)
Special Courses
• Health and Safety Plan Womshop (165.12)
• Designs for Air Impact Assessments at Hazardous Waste Sites (165. 16)
• Removal Cost Management System (165.17)
• Inland Oil Spills (165.18)
Courses Offered in Conjunction with Other EPA Offices
“ Chemical Emergency Preparedness and Prevention Office (CEPPO)
• Chemical Safety Audits (165.19)
/ Site Assessment Branch
• lntroducto y Preliminarj Assessment Training
• lntroductorj Site Investigation Training
• Federal Facilities Preliminary Assessment’S/fe Investigation
• Hazard Ranking System
• Hazard Ranking System Documentation Record
01198
page 10
Sampling fc Hazardous Matonals
Onen Don and IrmodUction
-------
Notes:
01190
S mpdng tw H.zardoul SAatcs aIu 11
Cnen om arid ln oductpon
-------
Course Goals
• Select the appropriate tools and methods for sampling surface water
and sediments.
• Describe the basic methods of soil sampling in the unsaturated zone.
• Demonstrate the proper method for obtaining a groundwater sample
from a monitoring well.
• Complete the required documentation, including chain of custody
and sample labels, for shipment of environmental samples to an
analytical laboratory.
• Complete fundamental tasks in a sampling event from initial site
investigation through field data collection.
01198
paje 12
• Select the appropriate field screening method for a given
contaminant and geologic environment.
• Select the appropriate sampling container and sample preservation
method based on the sample media and analysis required.
• Select the appropriate sampling implements and methods for
sampi ing various containerized wastes.
S pIing or Haza,dous Maten i•
and Inboducb n
-------
Notes:
Samp1rn lo Hazirdous Mat&taIs 01196
owtanon a, p$9S 13
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About the Agenda
• Agenda times are only approximate. Every effort is made to complete units and to finish
the day at the specified time.
• Class begins promptly at 8:00 a.m. on Tuesday. Please arrive on time to minimize
distractions to fellow students.
• Ten-minute breaks are given between units.
• Lunch is 1 hour.
Points to Remember
• Attendance at each lecture and exercise is required in order to receive an EPA course
completion certificate.
• Direct participation in field or lab exercises is optional. Roles for field exercises are
randomly assigned to ensure fairness.
• Every student must take the examination given on Thursday.
sampling ot Hazardous Matnals 01198
Onen on and Introdu iOn 14
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Notes:
oiioe
Sanipflrig fc Hawdous 15
One bon and OduC On
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CHEMICALS USED IN THIS COURSE
• Methanol • Nitric acid
• Hydrochloric acid • Succinic acid
• Tris (hydroxymethyl. • Tartaric acid
aminimethane) • Potassium chloride
• Isopropanol • Ethylenediaminetetraacetic acid,
• Napthalene disodium salt, dihydrate
• Ethanol • Indigo carmine
• Sulfuric acid • Diethylene glycol
• Oxalic acid • Sodium potassium tartrate,
• Acetone tetrahydrate
• Ammonium hydroxide
CHEMICALS USED IN THIS COURSE (cont.)
• Mercuric (II) iodide • Imidazole
• Glycerin • Sodium hydroxide
• Bovine serum albumin • Meso-tetra (4-N-
• Sodium methylpyridyl) porphine
• Mercuric nitrate in water teratosylate
• Organosulfur compound • Lead nitrate
• Bathocuproine • Potassium hydrogen phthalate
• Sodium bisulfite • Potassium hydroxide
• Glacial acetic acid • Potassium iodide
• Potassium nitrate, anhydrous • Sodium borate, decahydrate
For your safety, please speak with the course director regarding
any health concerns that may prohibit your direct participation in
exercises or labs involving use or close proximity to these
chemicals. Material Safety Data Sheets (MSDS) are available for
review.
Chemical Use and Health-related Considerations
For the Field Screening and Field Sampling exercises, gloves will be furnished Please wear gloves and
avoid ingestion, inhalation, and skin contact with these chemicals.
Sampling oq Hazardous Matenals
Oi eni iion and lnt,oducpon
01196
page 10
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Notes:
Sampling ør N,zardojs Matsnil, C1i
Onen Uon and Intjcdu on pagn Il
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About the Training Evaluation
The Training Evaluation is a tool to collect valuable feedback from YOU about this
course.
We value YOUR comments!! Important modifications have been made to this course
based on comments from previous students.
DO DON’T
Complete an evaluation at the end of • Hold back!
each unit!
• Focus exclusively on the presentation
• Tell us if you feel the content of the skills of the instructors.
course manual is clear and complete!
• Write your name on the evaluation if
• Tell us if you feel the activities and it will inhibit you from being direct
exercises were useful and helpful! and honest.
• Tell us if you feel the course will help
you perform related duties back on the
job!
• Complete the first page of the
evaluation at the end of the course
before you leave!
• Write comments in ink.
Sampling foiHaza,dou a Matenals 01100
Onentabon and Inbvducdon page 18
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Notes :
S.mpIiri ot M zardo ,s M&tsn.Is 01190
page 19
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Facility In formation
Please put beepers in the vibrate mode
and turn off radios. Be courteous to
fellow students and minimize
distractions
Emergency
Telephone
Numbers
Emergency Exits
Alarms
Sirens
to, -bzardoui Mate,*a?.
.o. .nd InOoducbod
01196
page 20
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Notes:
o i /96
Sampl&hg Hizirdoul M$tS U
Orienlatioi and Infroducbon
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Section 2
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SAMPLE PLAN DEVELOPMENT
STUDENT PERFORMANCE OBJECTIVES
At the conclusion of this unit, students will be able to:
1. Identify sources of background information
2. List and describe the 7-step data quality objectives (DQO)
process
3. Describe advantages and disadvantages of the various sample
designs discussed during the lecture
4. Identify proper containers, holding times, and detection
limits for the selected media
5. Select the proper standard operating procedure for the media
6. Determine appropriate quality assurance requirements for the
media selected
7. Describe the data validation process
8. Determine appropriate deliverables, given media and quality
assurance level
9. Describe the organization and responsibilities of the sampling
team.
NOTE : Students may use all references and material provided
in the course, unless otherwise specified, to perform
the objectives. Students are expected to perform each
objective without error.
11%
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SAMPLE PLAN
DEVELOPMENT
ELEMENTS OF A SAMPLING PLAN
• Background
• Data use objectives
• Sampling design
• Sampling and analysis
• Standard operating procedures
• Quality assurance requirements
ELEMENTS OF A
SAMPLING PLAN (cont.)
• Data validation
• Deliverables
• Project organization and
responsibilities
• Schedule of activities
• Attachments
1/96 1 Sample Plan-Development
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BACKGROUND
• Federal, state, and local files
• Interview former employees, residents
• Potentially responsible party (PRP)
BACKGROUND (cont.)
• Maps
• Facility building plans
• Aerial photographs
SANBORN FIRE INSURANCE MAPS
.1869 to 1950s
• Communities over 2000 population
• Updated periodically
• Locations of industries, pipelines, storage vats,
old dumps, and wetlands
Sample Plan Development
2
1/96
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AERIAL PHOTOGRAPHY
• Historical photography
(1920-present)
• Contract photography
(current site)
U.S. DEPARTMENT OF
AGRICULTURE
• USDA Farm Service Agency
Aerial Photography Field Office
801-975-3503
• 1945-present
black and white
color infrared
PURPOSE OF SAMPLING
• Remedial investigation!
feasibility study (RI/ES)
• Removal
• Risk assessment
• Site assessment
1/96 3 Sample Plan Development
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WHAT IS THE DATA QUALITY
OBJECTIVES (DQO) PROCESS?
Series of planning steps designed to
ensure that the type, quantity, and
quality of environmental data used in
decision making are appropriate for
the intended application
Sample Plan Development
4
1/96
-------
THE DQO PROCESS
Li . Ist t € , rpb1 m
1 _____
2. Identify the decision’
idi iifytnpuis to the deci on
4. Define the study boundaries
s p
7. Optimize the design for
obtaining data
11% 5 Sample Plan Development
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WHAT ARE DQOs?
Qualitative and quantitative statements that:
- Clarify the objectives
- Define appropriate data
• Determine appropriate conditions to
collect data
- Specify acceptable levels of errors
WHY DEVELOP DOCUMENT FOR
SUPERFUND?
• Mandatory QA requirements established in
EPA Order 5360.1
- NCP 40 CFR Part 300
- SAP/QAPP ç rô c pro e} fr
BENEFITS OF DQOs
• Improves sampling and analysis designs
• Saves money and time
• Improves decision making
Sample Plan Development 6 1/96
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MORE INFORMATION?
• Contact: Duane Geuder
QA Manager for OERR
703-603-8891
• Training: EPA Institute
202-260-3297
QUALITY ASSURANCE OBJECTIVES
Parameters Matrix Intended Data Use
BNA (semivolatiles) Drum liquid Site characterization
Metals Groundwater Risk assessment
Metals Potable water Risk assessment
PAHs Soil Site characterization
PAHs Waste material Site characterization
1/96 7 Sample Plan Development
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SAMPLING METHODOLOGIES
Sampling design:
• Judgmental
• Random sampling
• Stratified random sampling
• Systematic sampling
• Systematic random sampling
JUDGMENTAL SAMPLING
The subjective selection of sampling
locations at a site, based on historical
information, visual inspection, and the
best professional judgment of the
sampling team
RANDOM SAMPLING
Adapted from U S EPA 969 Metho br Evalua Q the Attainment Of Cleanup Slandarcle
Volume 1 SoIls and Sold Media
Sample Plan Development
8
1/96
-------
STRATIFIED RANDOM SAMPLING
lt
75
25
C
(1 25 50 75 ICO 125 150 175
da ted from US EPA. 1960 Metho to, AiaUng the nmeni ot Cleanup
Slarldar . Volume 1 Solli and Sold Meia
SYSTEMATIC SAMPLING
t,toS
Adapted Irom U S EPA. 1969 Melho br Evaluath the Allalnrnenl ot Cleanup
Standar Volume 1 Salle and Sold M&la
RANDOM SYSTEMATIC SAMPLING
The area is first subdivided into a grid
as described in systematic sampling.
Then samples are collected from within
each cell using random selection
procedures.
1/96
9
Sample Plan Development
-------
SAMPLING METHODOLOGIES
Sampling Equipment
Sampling Fabrication Decontamination
Parameters/Matrix Equipment Use Dedicated Steps
BNA (semivolatiles) COLIWASA Glass No Physical removal
Nonphosphate
detergent wash
Potable water rinse
10% nitric acid rinse
Organic-free water
rinse
Air dry
Metals in groundwater Bladder pump Stainless steel Yes
Sample Plan Development 10 1/96
-------
SAMPLING METHODOLOGIES
Standard Operating Procedures
• Agency standard operating procedures
• Region standard operating procedures
• Other federal agency regulations
SAMPLING METHODOLOGIES
Standard Operating Procedures (cont.)
Minimum that should be addressed:
- Field documentation
- Sampling standard operating procedures
- Shipping and handling
QUALITY ASSURANCE/QUALITY
CONTROL (QA/QC) GOALS
• Define requirements from the Quality
Assurance Objectives
• Refers back to the QA Objectives and
parameters identified in the plan
• Identify and implement correct sampling
and analysis methods
• Limit the error introduced into the sampling
and analysis procedure
1/96 11 Sample Plan Development
-------
QA/QC SAMPLES
• Analyze in addition to field samples
• Provide information on variability
and usability of data
I
RINSATE BLANKS
(Equipment Blanks)
Obtain by running analyte-free
deionized water over decontaminated
sampling equipment
Test for residual contamination
TRIP BLANKS
• Prepare prior to fieldwork
• Use certified clean sand or soil or
analyte-free deionized water
• Test for residual contamination
Sample Plan Development
12
1/96
-------
TRIP BLANKS (cont.)
Assess error associated with
• Sampling
• Sample handling and shipping
• Laboratory handling and analysis
MATRIX SPIKE SAMPLES
• Field sampling
- Collect triple the volume for organ c water
samples
- Collect double the volume Iorj ç ni
water samples
• Laboratory analysis
- Use selected or requested field samples
- Spike samples in the laboratory with
known concentrations of target analytes
MATRIX SPIKE SAMPLES (cont.)
• Verify percent recoveries
• Check sample matrix interferences
• Monitor laboratory and method
performance
1/96
13
Sample Plan Development
-------
FIELD REPLICATES
• Samples obtained from one location and
divided into separate containers
• Treated as separate samples
• Used to assess laboratory error and sampling
methodology error
• May be used as a split sample for PRP
investigations
DATA VALIDATION
-ç Describes the steps for data validation
. J I and states the criteria for each of the
procedures
DELI VERABLES
Describes the final product
or outcome of the sampling
event
Sample Plan Development 14 1/96
-------
ORGANIZATIONAL STRUCTURE
Designates the organizational structure
of the sampling teams and defines
responsibilities of onsite personnel
and supporting agencies
SUMMARY
• Review historical information
• Perform site reconnaissance
• Evaluate migration pathways and receptors
• Determine sampling objectives
• Establish data quality objectives
SUMMARY (cont.)
• Select field screening techniques
• Select analytical parameters
• Select sampling approach
• Determine sampling locations
1/96 15 Sample Plan Development
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What is QASPER”
QAS PER is a PC-based software package which compites
generic text and user-provided site-specific information
into a draft Quality Assurance / Quality Control (OA/QC)
Sampling Plan for the Removal Program QASPER ad-
dresses the nine sections of a QAJQC Sampling Ptan as
specified in OSWER Directive 9360 4-01, OA/OC
Guidance for Removal A tiviiics, Sampling QAJQC Plan,
and Data Validation Procedures (April 1990, EPAJ54O/G-
90/004)
Who is the Anticipated QASPER User?
The On-Scene Coordinators (OSCs) or the Technical As-
sistance Team (TAT) contractors arc the primary users of
QASPER These individuals wilt have access to the site-
specific information and the sampling objectives thai char-
acterize the site They are also the ones responsible for
assembling that information into an acceptable game plan
for implementation.
Why was QASPER Designed?
QASPER was created to facilitate the timely assembly of a
comprehensive sampling plan for emergency response ac-
tions By thorough consideration and attention to the
necessary requirements of QA/OC sample planning
through an automated process, it is anticipated that reli-
able, accurate, and quality data will be generated to meet
the intended use
Requirements
OASPER runs on an IBM PC or 100% compatible, with a
hard drive, 640K RAM, and a printer (for hardcopy out-
Put)
Features of QASPER
• Requires no other software for support A word
processing package is included with the QASPER
program
• Generates ASCII output in both file and hardcop
formats Files may be uploaded to oilier word
processing packages (i e , WordPerfect) (or fur-
ther manipulation
• Creates a hard copy QA/QC Sampling Plan rcath
for approval signatures and implementation
• Retains database files on all previous sampling
plans created This allows for future manipulation
of an existing plan without having to recreate the
document or search for a similar sampling plan by
location, facility type, or contaminant
• Improves the consistency and comprehensiveness
of sampling plan creation efforts throughout the
office, region, or zone by prompting the user to
consider the same set of questions lot each site to
be addressed
• Improves cfliciencv for creating and reviewing
OAIOC Sampling Plan documcntsbv ziltosvingc.tcy
modification of the document text iithcr tltrouch
the cditor or through the word proccssing p ckagc
• Picks up information that has repetitive usi.. in the
plan and imports the inlormation to all sections
after the first entry, thus avoiding redundant data
entry -
• Providcc the user tb access to ciand.irdi,cd
generic text iii various sections of ilti plan B.iscd
on the user’s needs, this text niav bc ini 1 rnrtcd
directly or may be cdiicd to fit sitc-spLclflc LI .ifl(lI-
tions
United Siates
Environmenial Protection
Agency
Of ice of
Solid Waste and
Emergency Response
January 1992
QualityAssurance
TEAM /
Sampling Plan for
Emergency Response
Othce of Emergency and Remedial Response
Emergency Response Division
Environmental Response Branch, MS-lot
Quality Assurance Technical
lnloimaiion Bulletin
1/96
17
Sample Plan Development
-------
• Has flexible data entry throughout plan generating
activities and informs thc user as to which sections
are complete and which sections require addition-
al information.
Contents of QASPER
QASPER addresscs the nine sections of a OA/OC Sam-
pling Plan, as specified in OSWER Directive 93604-01,
QA/OC Guidance for Removal Activities, Sampling
OA/OC Plan and Data Validation Procedures
0.0 Title Page Information
Section 00 identilics information required to
complete the title pagc cia sampling plan This
information includes site name, relevant work
order numbers, primary site personnel and tit-
les, and the date Some of this information is
utilized elsewhere throughout the plan and will
automatically appear in the proper places
1 0 Background Information
Section 1 0 solicits background information
about the site This includes the location and
type of facility, type and volume of materidl
handled by the facility, current facility status and
proximity and type of sensitive environments
2.0 Data Use Objectives
Section 2 0 requests information regarding the
data use objectives and about decisions the data
will support. The purpose(s) of the sampling
event is specified and this information is for.
warded to other sections of the plan The data
qualityobjective (DOO) logic pathway begins in
this Section and is carried forward to Sections
3.0, 4 0, 60 and 8 0
3.0 Quality Assurance Objectives
Section 3.0 facilitates the linkage of the DQO
logic with the matrix and parameters being in-
vestigated The user must also specify the pur-
pose and QA objective (OA-1, OA-2, or QA-3)
related to the selection The same sequence will
be repeated for all parameters of concern t the
SitC
4 0 Approach and Sampling Methodologies
Section 4.0 addresses the approach and sam-
pling methodologies that will be employed In-
cluded are sections on sampling equipment,
sampling design, standard operating proce-
dures, schedule of activities and tables
In the case of equipment, there arc pull down
menus for type of equipment and materials of
construction Where dedicated sampling
equipment is not utilized, QASPER assists in
the development of a decontamination se-
quence The sampling design Section requires
the . user to input information relattd to the
proposed design or grid to achic c the s.implc
event objectives In conjunction ‘ith the sam-
pling design, the user must specify the standard
operating procedures (SOPs) th it will be
cmploycd QASPER contains generic tc t for
approximately 20 SOPs that can be imported as
is or modified to fit a specific scenario A
schedule of activities detailing site activities and
tentative start and completion dates is in the next
section The last components of this sect ion arc
the sample summary tables and OC sample
tables
5 0 Project Organization and Responsibilities
Section 50 helps the user organize information
about what personnel are assigned which respon-
sibilities and which labs will be analyzing which
samples.
6 0 QA Requirements
Section 6.0 is automatically completed based on
the QA selections made in Section 3 0
Capabilities exist to edit the generic tc’a as
needed
7.0 Deliverables
Section 70 allows the user to import gencric text
for standard deliverables that will be prepared
for the Site or input specific requirements
8.0 Data Validation
Section 8 0 contains the requirements for validat-
ing the data generated under this plan as per
OSWER Directive 9360 4-01, Part it, Data
Validation Procedures(April , 1990) The criteria
used ensure that analytical results received from
the laboratory are valid and accurate for the
objective chosen. The section is automatically
completed based on the QA selections made in
Section 3.0. Capabilities exist to edit the generic
text as needed
Once all the sections are eompleted, the user can compile
the plan, make any necessary modifications, and print a
hard copy of the site-specific OAIOC Sampling Plan
For copies oft/ic sofrware, Contact
Mr. William Coakle-y
US EPA, ERT
Flio,ic (908) 906-6921
Ms C’hns:ine Andrea:
Roy F Weston, Inc IREAC
Phone (908) 632-9200
NOTE: The above phone numbers are no longer
valid Please call 908-321-4398 for copies of
QASPF_R, or mail the form on the following page
Sample Plan Development
18
1/96
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Environmental Response Center
US EPA - ERT
2890 Woodbridge Avenue
Building #18 (MS 101)
Edison NJ 08837-3679
1400-999-6990
p OU). e r4 -
Distribution Request Form
Name: ______________________ Date:
Company:
Street:
City/State/Zip:
Telephone: ( )
1 pc ct Bans (aS. an): Federal—State---Local —Private
or Other:
Order Taken By: Class Given By:
Environmental Utilities Software Packages:
Title Ouantity
Air Methods Database
Field Certification Tracking
System (FCTS 9285.3-03)
Health and Safety Plan
(HASP 9285.801)
Quality Assurance Sampling
Plan for Environmental Response
(QASPER)
(Da.tr&RnçtatFRM 12)95)
11% 19 Sample Plan Development
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Sampling QA/QC Work Plan
Example Sample Plan
Prepared by
Amazing Consultants
EPA Project No.:
Contractor Work Order No.: NA
EPA Contract No.: NA
Approvals
Amazing Consultants EPA
Date O.S. Cee Date
Task Leader On-Scene Coordinator
Fred Amazing Date
Project Manager
1/96 21 Sample Plan Development
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1.0 BACKGROUND
The [ suspected] contamination is a result of:
Leaking drums
The following information is known about the site:
The site is located in the city of Swartz Creek in the county of Genesse in the state of Michigan
(Figure 1-1). The nearest residents are located within 500 feet of the site, in a south direction.
Other residents or significant environments in proximity to this site are located 1000 feet due north
of the site
It is a landfill site on an unknown number of acres which had been operating for an unknown period
of time and is now abandoned since 1980.
The types of material(s) handLed at this site were:
• Inorganics
• Petroleum products
• Unknown
The volume(s) of contaminated materials to be addressed are:
• Unknown
The contaminants of concern are:
• Unknown
The basis of this information may be found from:
• Citizens
• Records
1/96 23 Sample Plan Development
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Example Sample Plan
Figure 1-1 Site Location Map
Sample Plan Development 24 1/96
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2.0 DATA USE OBJECTIVES
The objective of this project/sampling event is to determine.
• The presence of contamination
• The extent of contamination
• The magnitude of contamination
For the purpose of:
• Site characterization
• Risk assessment
• Field personnel health and safety
• Enforcement plan
The data will be evaluated against:
• Federal/state action levels
• Michigan and federal ARARs
1/96 25 Sample Plan Development
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3.0 QUALITY ASSURANCE OBJECTIVES
As identified in Sections 1.0 and 2 0, the objective of thLs project/event applies to the following
parameters:
Parameters Matrix Intended Data Use GA Objective
BNA {semivolatures} Drum liquid Site characterization GAl
Metals Groundwater Risk assessment QA3
Metals Potable water Risk assessment 0A3
PAHs Soil Site characterization 0A2
PAHs Waste rnateriat Site characterization 0A2
Sanzple Plan Development 26 1/96
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4.0 APPROACH AND SAMPLING METHODOLOGIES
4.1 Sampling Equipment
The following equipment will be used to obtain environmental samples from the respective
medialmatrix:
Sampling
Parameter/Matrix Equipment Fabrication Dedicated Decontamination Steps
BNA COLIWASA Glass No Physical removal
(semivolatiles) Nonphosphate detergent
wash
Potable water rinse
1 0% nitriC acid rinse
Organic-free water rinse
Air dry
Metals in Bladder pump Stainless steel Yes
ground water
Metals in potable Sample bottle Glass Yes
water
PAHs in soil Tiowel Stainless steel No Physical removal
Nonphosphate detergent
wash
Pesticide-grade acetone
rinse
Distilled/deionized water
rinse
Organic-free water rinse
Air dry
PAHs in waste Bucket auger Stainless steel No Physical removal
material Nonphosphate detergent
wash
Potable water rinse
10% nitric acid rinse
Distilled/deionized water
rinse
Organic-free water rinse
Air dry
4.2 Sampling Design
The sampling design is depicted on the attached Sample Location Map (Figure 4-1) and is based on
the following rationale:
1/96 27 Sample Plan Development
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Example Sample Plan
Figure 41 Sample Location Map
Swqile Plan Development 28 1/96
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4.3 Standard Operating Procedures
4.3.1 Sample Documentation
All sample documents will be completed legibly, in ink. Any corrections or revisions will be made
by lining through the incorrect entry and by initialing the error.
Field Logbook
The field logbook is essentially a descriptive notebook detailing site activities and observations so
that an accurate account of field procedures can be reconstructed in the writer’s absence. All entries
will be dated and signed by the individuals making the entries and should include (at a minimum)
the following:
1. Site name and project number.
2. Name(s) of personnel onsite.
3. Dates and times of all entries (military time preferred).
4. Descriptions of all site activities, including site entry and exit times.
5. Noteworthy events and discussions.
6. Weather conditions.
7. Site observations.
8. Identification and description of samples and locations.
9. Subcontractor information and names of onsite personnel.
10. Date and time of sample collections, along with chain-of-custody information.
11. Record of photographs.
12. Site sketches.
Sample Labels
Sample labels will clearly identify the particular sample and should include the following:
1. Site name and number.
2. Time and date sample was taken.
3. Sample preservation.
4. Analysis requested.
Optional, but pertinent, information is the sample location.
Sample labels will be securely affixed to the sample container. Tie-on labels can be used if properly
secured.
1/96 29 Sample Plan Development
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Chain-of- Custody Record
A chain-of-custody record will be maintained from the time the sample is taken to its final
deposition. Every transfer of custody must be noted and signed for, and a copy of this record kept
by each individual who has signed. When samples (or groups of samples) are not under direct
control of the individual responsible for them, they must be stored in a locked container sealed with
a custody seal.
The chain-of-custody record should include (at minimum) the following:
1. Sample identification number.
2. Sample information.
3. Sample location.
4. Sample date.
5. Name(s) and signature(s) of sampler(s).
6. Signature(s) of any individual(s) with control over samples.
Custody Seals
Custody seals demonstrate that a sample container has not been tampered with or opened.
The individual in possession of the sample(s) will sign and date the seal, affixing it in such a manner
that the container cannot be opened without breaking the seal. The name of this individual, along
with a description of the sample packaging, will be noted in the field logbook.
4.3.2 Sampling SOPs
Drum Sampling
Prior to sampling, drums must be inventoried, staged, and opened. Inventory entails recording
visual qualities of each drum and any characteristics pertinent to the contents’ classification. Staging
involves the organization, and sometimes consolidation, of drums which have similar wastes or
characteristics. Opening of closed drums can be performed manually or remotely. Remote drum
opening is recommended for worker safety.
The most widely used method of sampling a drum involves the use of a glass thief. This method
is quick, simple, relatively inexpensive, and requires no decontamination. The thief is inserted into
the drum until a solid layer or bottom of the drum is encountered. The waste is allowed to
equilibrate in the sample tube, which is then capped and removed for discharge by gravity into the
sample container.
Another drum sampling device is the Composite Liquid Waste Sampler (COLIWASA). Collection
with a COLIWASA allows a sample to be collected from the full depth of a drum and maintain it
in the transfer tube until delivery to the sample bottle. The COLIWASA is designed to permit
representative sampling of multiphased wastes from containerized wastes. However, unlike the glass
Sample Plan Development 30 1/96
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thief, a COL [ WASA is extremely difficult to field decontaminate arid relatively expensive, thereby
making it impractical to throw away.
Groundwater Well Sampling
Prior to sampling a well, the well will be purged. For this project, purging will be accomplished
with a [ (bailer), (submersible pump), (non-gas contact bladder pump), or (suction pumps)]
First, brush off the well cap prior to opening, then unlock and open the well cap. A photoionization
detector (HNU) or flame ionization detector (OVA) will be used on the escaping gases to determine
the need for respiratory protection. Using a decontaminated water level indicator, the water level
will be measured to the nearest 0.01 ft Total depth of the well will be obtained with a depth
sounder and the volume of water in the well will be calculated using the following procedure:
Well Volume = nr2h (7.48 gall ft 3 )
where:
= pi
r = radius of well casing in ft
h = height of water column of well from water level
7.48 = conversion from ft 3 to number of gallons
At a minimum, three well volumes should be purged if possible. Equipment must be decontaminated
both prior to use and between wells
Approximately 10 ft of plastic sheeting will be placed around the well. The assembly of the
decontaminated purging equipment will be placedon this sheeting. The assembly will be lowered into
the well to a point just below the surface of the water.
When pumping the well, lower the pump slowly to a point 3 ft above the bottom of the well. Record
the flow rate and calculate the length of pumping time required to purge the requisite three casing
volumes. [ Discharged to ground surface adjacent to the well or containerized if necessary.1 If the
well yield is insufficient to produce the requisite three volumes, purging will continue to the point
of well evacuation and then terminated; the well will be sampled upon recharge.
Once purging is completed and the correct sample jars andlor vials have been prepared, sampling
will proceed. The sampling device (which may or may not be the same as the purging device) has
been selected so as to not affect the integrity of the sample. Sampling equipment will be
decontaminated as outlined elsewhere in Section 4.0. Sampling will occur in a progression from the
least to most contaminated well, if known.
The water sample will be collected using a Teflon or stainless steel bailer. The bailer will be
attached to a clean, dedicated, nylon rope and introduced into the well. The bailer will be lowered
to the approximate mid-point of the screened interval. Once the sample is collected, care will be
taken not to unduly agitate or aerate the water while pouring into the appropriate sample containers.
1/96 31 Sample Plan Development
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Measure the conductivity, temperature, and pF! of the groundwater in a separate container. Record
all field measurements on the field data sheets and in the field logbook.
Potable Water Sampling
Potable water samples will be collected from the discharge spigot nearest the pump. Water will be
purged from the system for approximately 15 minutes to remove all standing water in the holding
tank. Any aerators or filtering systems will be bypassed if possible. Samples will be collected
directly into sample bottles from the spigot. Samples will be iced and packaged in coolers as per
the applicable shipping and handling SOPs.
Soil Sampling
(This text requires modification for site-specific application)
Collection of samples from near-surface soil will be accomplished with tools such as spades, shovels,
and scoops. Surface debris will be removed to the required depth with this equipment, then a
stainless steel or plastic scoop can be used to collect the sample. This method can be used in most
soil types but is limited to sampling near surface areas. The use of a flat, pointed mason trowel to
cut a block of the desired soil can be helpful when undisturbed profiles are required. A stainless
steel scoop, lab spoon, or plastic spoon will suffice in most other applications.
Sampling a depth will be accomplished with augers and thin-walled tube samplers. This system
consists of an auger, a series of extensions, a “T” handle, and a thin-walled tube sampler. The auger
is used to bore a hole to the desired sampling depth and is then withdrawn. The auger tip is then
replaced with a tube core sampler, lowered down the borehole, and driven into the soil at the
completion depth. The core is then withdrawn arid the sample is collected. Several augers are
available. These include bucket type, Continuous flight (screw), and post hole augers. Bucket types
are better for direct sample recovery because they provide a large volume of sample in a short time.
When continuous flight augers are used, the sample can be collected directly off the flights, which
are usually at 5-ft intervals. The Continuous flight augers are satisfactory for use when a composite
of the complete soil column is desired. Post hole augers have limited utility for sample collection
because they are designed to Cut through fibrous, rooted, swampy soil.
Depth samples will be collected via split spoon samplers. A series of consecutive cores may be
sampled to give a complete soil column, or an auger may be used to drill down to the desired depth
for sampling. The split spoon is then driven to its sampling depth through the bottom of the augured
hole and the core is extracted.
Subsurface soil sample collection will involve test pit/trench excavation activities. Test pits and
trenches are used for detailed examination of soil characteristics. Samples are collected from the pit
using a trowel scoop or coring device.
All sampling devices should be laboratory cleaned, preferably by the laboratory performing the
analysis, using pesticide grade acetone (assuming that acetone is not a target compound) or methanol,
then wrapped in cleaned and autoclaved aluminum foil, and custody sealed for identification. The
Sample Plan Development 32 1/96
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sampling device should remain in this wrapping until it is needed. Each sampler should be used for
one sample only. However, dedicated samplers may be impractical if there are a large number of
soil samples required. In this case, samplers should be cleaned in the field using the decontarmnation
procedure described elsewhere in Section 4.0.
4.3.3 Sample Handling and Shipment
Each of the sample bottles will be sealed and labeled according to the following protocol. Caps will
be secured with custody seals. Bottle labels will contain all required information including site name
and sample number, time and date of collection, analysis requested, and preservative used Sealed
bottles will be placed in large metal or plastic coolers, and padded with an absorbent material such
as vermiculite.
All sample documents will be affixed to the underside of each cooler lid. The lid will be sealed and
affixed on at least two sides with custody seals so that any sign of tampering is easily visible.
4.4 Schedule of Activities
The proposed schedule of work is provided in the following table:
Activity
Start Date
End Date
Soil sampling
07/28/93
08/10/93
Potable water sampling
07/28193
08/10/93
Groundwater sampling
08/10/93
09/10/93
Drum sampling
08/10/93
11/22/93
1/96 33 Sample Plan Development
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5.0 PROJECT ORGANIZATION AND RESPONSIBILITIES
The EPA On-Scene Coordinator, O.S. Cee, will provide overall direction to Amazing Consultants
staff concerning project sampling needs, objectives, and schedule.
The Amazing Consultants Task Leader, _________________ , is the primary point of contact with
the EPA On-Scene Coordinator. The Task Leader is responsible for the development and completion
of the Sampling QAIQC Plan, project team organization, and supervision of all project tasks,
including reporting and deliverables.
The Amazing Consultants Site QC Coordinator, _________________ , is responsible for ensuring
field adherence to the Sampling QA/QC Plan and recording any deviations. The Site QC
Coordinator is also the primary project team contact with the analytical laboratory.
The following sampling personnel will work on this project:
Personnel
Responsibility
The following laboratories will be performing the analyses listed below:
Laboratory Name/Address
Type of Laboratory
Parameters
Amazing Analytical Lab
1 23 Reading Road
Pittsburgh, KN
Non-CLP
All
Sample Plan Development 34 1/96
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6.0 QUALITY ASSURANCE REQUIREMENTS
The requirements detailed in this section apply to the respective QA objectives and parameters
identified in Section 3.0.
The following QA protocols for QA2 data are applicable to all sample matrices and include:
1. Provide sample documentation in the form of field logbooks, the appropriate field
data sheets and chain-of-custody records. Chain-of-custody records are optional for
field screening locations.
2. All instrument calibration and/or performance check procedures/methods will be
summarized and documented in the field/personal or instrument log notebook.
3. The detection Limit wilt be determined and recorded, along with the data, where
appropriate.
4. Document sample holding times; including documentation of sample collection and
analysis dates.
5. Provide initial and continuing instrument calibration data.
6a. For soil, sediment, and water samples, include rinsate blanks, field blanks, and trip
blanks, as specified in the attached table.
6b. For air samples, include lot blanks, field blanks, collocated samples, trip blanks,
breakthrough, and QC positive samples, as specified in the attached table.
7. Performance Evaluation samples are optional, if available.
8. Choose any one or combination of the following three options:
(1) Definitive identification - confirm the identification of analytes on 10% of the
screened (field or lab) or 100% of the unscreened samples via an
EPA-approved method; provide documentation such as gas chromatograms,
mass spectra, etc.
(2) Quantitation - provide documentation for quantitative results from screening
and the EPA-approved verification method (for screened samples) or just the
quantitative results (in the case of unscreeried samples).
(3) Analytical error determination - determine the analytical error by calculating
the precision, accuracy, and coefficient of variation on a subset of the
screened or all of the unscreened samples using an EPA-approved method.
1/96 35 Sample Plan Development
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The following QA Protocols for QA3 data are applicable for all matrices and include:
1. Provide sample documentation in the form of field logbooks, the appropriate field
data sheets, and chain-of-custody records. Chain-of-custody records are optional for
field screening locations.
2. All instrument calibration and/or performance check procedures/methods will be
summarized and documented in the field/personal or instrument log notebook.
3. The detection limit will be determined and recorded, along with the data, where
appropriate.
4. Document sample holding times; including documentation of sample collection and
analysis dates.
5. Provide initial and continuing instrument cahbration data.
6a. For soil, sediment, and water samples, include rinsate blanks, field blanks, and trip
blanks, as specified in the attached table.
6b. For air samples, include lot blanks, field blanks, collocated samples, trip blanks,
breakthrough, and QC positive samples, as specified in the attached table.
7. Performance Evaluation samples are required.
8. Definitive identification on 100% of the TM critical M samples by an EPA-approved
method.
9. Quantitation - provide documentation for quantitative results from screening and
EPA-approved verification methods (for screened samples) or just quantitative results
(in the case of unscreened samples).
10. Analytical error determination on 100% of the “critical” samples by an
EPA-approved method. Determine precision, accuracy and coefficient of variation.
Determine false-positive and false-negative values.
Sample Plan Development 36 1/96
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7.0 DELIVERABLES
The Amazing Consultants Task Leader, ___________________ , will maintain contact with the EPA
On-Scene Coordinator, O.S. Cee, to keep him/her informed about the technical and finaiIcial
progress of this project. This communication will commence with the issuance of the work
assignment and project scoping meeting. Activities under this project will be reported in status and
trip reports and other deliverables (e.g., analytical reports, final reports) described herein. Activities
will also be summarized in appropriate format for inclusion in monthly and annual reports.
The following deliverables will be provided under this project:
• Final Report
A (draft) final report will be prepared to correlate available background information with data
generated under this sampling event and identify supportable conclusions and recommendations which
satisfy the objectives of this sampling QA/QC plan.
1/96 37 Sample Plan Development
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8.0 DATA VALIDATiON
8.1 QA2
Data generated under this QAIQC Sampling Plan will be evaluated accordingly with appropriate
criteria contained in the Removal Program Data Validation Procedures which accompany OSWER
Directive #9360.4-1.
The results of 10% of the samples in the analytical data packages should be evaluated for all of the
elements listed in Section 6.0 of the QAIQC Sampling Plan. The holding times, blank
contamination, and detection capability will be reviewed for all remaining samples.
8.2 QA3
Data generated under this QA/QC Sampling Plan will be evaluated accordingly with appropriate
criteria contained in Removal Program Data Validation Procedures which accompany OSWER
Directive #9360.4-1.
This objective, the most stringent of all objectives, requires that at least 10% of the samples in the
laboratory data package be evaluated for all of the elements listed in Section 6.0 of this QA/QC
Sampling Plan Of the remaining samples, holding times, blank contamination, precision, accuracy,
error determination, detection limits, and confirmed identification will be reviewed. This objective
also requires review of all elements for all samples in each analyte category (i.e., VOAs and PCBs)
in every tenth data package received from an individual laboratory.
Sample Plan Development 38 1/96
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FIELD SAMPLING SUMMARY
Container
Performance Total
Analytical Level of Type and Holding Subtotal Rinsate Trip Evaluation Matrix Field
Parameter Sensitivity Matrix Volume Quantity Preservative Time Samples Blanks Blanks (PE) Samples Spikes Samples
BNA 5 ppm Drum liquid 1-L amber 2 4C 7/40 days 100 NAb NA NA NA 100
semivola tiles glass
Metals 0.05 ppm Groundwater 1-L 1 HNO 3 to pH 6 months 20 2 NA 1 8 23
polyethylene <2; 4C
Metals 1 ppm Potable 1-L 1 HNO 3 to pH 6 months 20 2 NA 1 8 23
water polyethylene <2; 4C
PAHSC 0.01 Soil 8-oz. glass 1 4C 7/40 days 35 3 NA 0 2 38
mg/kg
PAHs 5 ppm Waste 8-oz. glass 1 4C NAd 100 NA NA NA NA 101
material
PAHs I ppm Waste 8 -az. glass 1 4C 7/40 days 101 1 NA 0 1 <11 >•
material
BNA - base, neutral, acid
b NA - not applicable
C PAH - polycyclic aromatic hydrocarbon.
d Field test (imniunoassay .
Confirmation samples sent to laboratory.
I
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TABLE 3. QAIQC ANALYSIS AND OBJECTIVES SUMMARY
I
Matrix Spike OAIQC
Analytical
Parameter
Matrix
Analytical Method
Reference
Laboratory
Additional
Detection Limits
QA Objective
DNA’
Drum J quid
8270
NAb
NA
See attachments
OAf
semivolatiles
Metals
Groundwater
SW846c
8
NA
See attachments
OA3
Metals
Potable water
SW-846
8
NA
See attachments
QA3
PAHSd
Soil
8100
2
NA
Analyte specific
0A2
PAHs
Waste matertal
lmmunoassav’
SW-846
NA
1
NA
NA
Analyte specific
Analyte specific
0A2
0A2
• BNA - base, neutral, acid.
b NA - not applicable.
SW-846 - U.S. EPA. 1986. Test methods fcw evaluating solid waste: physical/chemical methods FSW-846). U.S. Environmental
Protection Agency. Office of Solid Waste and Emergency Response. Washington, DC.
d PAH - polycyclic aromatic hydrocarbon.
• Used for field screening.
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TARGET COMPOUND LIST (TCL) AND
QUANTITATION LIMITS (QU’
Quantitation Limit?
Water
Low
Soil/SedimenV
Volatiles CAS Number (pg/L I
(pg/kg)
1. Ch loromethane 74-87-3 10 10
2. Bromomethane 74-83-9 10 10
3. Vinyl chloride 75-01-4 10 10
4. Chloroethane 75-00-3 10 10
5. Methylerie chloride 75-09-2 10 10
6. Acetone 67-64-1 10 10
7. Carbon disulfide 75-15-0 10 10
8. 1,1-Dichloroethene 75-35-4 10 10
9. 1 ,1-Dich loroethane 75-34-3 10 10
10. 1,2-Dichloroethene (total) 540-59-0 10 10
11 Chloroform 67-66-3 10 10
12. 1,2-Dichloroethane 107-06-2 10 10
13. 2-Butanone 78-93-3 10 10
14. 1,1,1-Trich loroethane 71-55 -6 10 10
15. Carbon tetrach loride 56-23-5 10 10
16. Bromodichloromethane 75-27-4 10 10
17. 1,2-Dichloropropane 78-87-5 10 10
18. cis-1,3-Dichloropropene 10061-01-5 10 10
19. Trichloroethene 79-01-6 10 10
20. Dibromochloromethane 124-48-1 10 10
21. 1,1,2-Trichloroethane 79-00-5 10 10
22. Benzene 71-43-2 10 10
23. trans-1,3-Dichtoropropene 10061-02-6 10 10
24, Bromoform 75-25-2 10 10
25. 4-Methyl-2-pentanone 108- 10-1 10 10
26 2-Hexanone 591-78-6 10 10
27. Tetrachloroethene 127-18-4 10 10
28. Toluene 108-88-3 10 10
29. 1 1 ,2,2-Tetrachloroethane 79-34-5 10 10
30. Chlorobenzene 108-90-7 10 10
31. Ethylbenzene 100-41-4 10 10
32. Styrene 100-42-5 10 10
33. Xylenes (total) 1330-20-7 10 10
Specific quantitation limits are highly matrix dependent. The quantitation limits listed herein are provided
for guidance and may not always be achievable.
Quantitation limits listed br soil/sediment are based on wet weight The quantitation limits calculated
by the laboratory for soil/sediment on dry weight basis will be higher.
C Medium Soil/Sediment Quantatation Limits (01) for Volatile TCL Compounds are 1 25 times the individual
Low Soil/Sediment CL
Based on the Contract Laboratory Program Statement of Work. OLMO 1 6 (6191)
1/96 41 Sample Plan Development
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TARGET COMPOUND LIST (TCL) AND
QUANTITATION LIMITS (QL)
Quantitalion Limitsb
Water
low
SodlSedimentc
Sem ivolatiies CAS Number (pg/I)
(pg/kg)
34. Phenol 108-95-2 10 330
35. bis(2-Chloroethyl)ether 111 -44-4 10 330
36. 2-Chlorophenol 95-57-8 10 330
37. 1,3-Dichlorobenzene 541-73-1 10 330
38. 1,4-Dich(orobenzene 106-46-7 10 330
39. 1,2-Dichlorobenzene 95-50-1 10 330
40. 2-Methylphenol 95-48-7 10 330
41. 2 2-oxybis(1 -Chloropropane) 108-60-1 10 330
42. 4-Methylphenol 106-44-5 10 330
43. N-N troso-di-n-propylaniine 621-64-7 10 330
44. Hexachloroethane 67-72-1 10 330
45. Nitrobenzene 98-95-3 10 330
46. Isophorone 78-59-1 10 330
47. 2-Nitrophenol 88-75-5 10 330
48. 2,4-Dimethylphenol 105-67-9 10 330
49. bis(2-Chloroethoxy)methane 111-91-1 10 330
50. 2,4-Dichlorophenol 120-83-2 10 330
51. 1,2,4-Tnchlorobenzene 120-82-1 10 330
52. Naphthalene 91-20-3 10 330
53. 4-Chloroaniline 106-47-8 10 330
54. HexachIorobutad ene 87-68-3 10 330
55. 4-Chloro-3-methylphenol 59-50-7 10 330
56. 2-Methylnaphtha ene 91-57-6 10 330
57. Hexachiorocyclopentadierie 77-47-4 10 330
58. 2,4,6-Trichlorophenol 88-06-2 10 330
59. 2,4,5-Trichlorophenol 95-95-4 25 800
60. 2-Chloronaphthalene 91-58-7 10 330
61. 2-Nitroaniline 88-74-4 25 800
62. Dimethylphthalate 131-11-3 10 330
63. Acenaphthylene 208-96-8 10 330
64 2,6-Dinutrotoluene 606-20-2 10 330
65. 3-Nitroaniline 99-09-2 25 800
66. Acenaphthene 83-32-9 10 330
67. 2,4-Dinitrophenol 51-28-5 25 800
68. 4-Nitrophenol 100-02-7 25 800
69. Dibenzofuran 132-64-9 10 330
70. 2,4-Dinitrotoluene 121-14-2 10 330
71. Diethylphihalate 84-66-2 10 330
72. 4-ChIoropheny -phenyl ether 7005-72-3 10 330
73. Fluorene 86-73-7 10 330
Sample Plan Development 42 1/96
-------
TARGET COMPOUND LIST (TCL) AND
QUANTITATION LIMITS (QL)’
Quantitation Limitsb
Water
Low Soil/Sediment 6
Semivolatiles (corit.)
CAS Number
(pgIL)
(pg/kg)
74. 4-Nitroaniline
100-01-6
25
800
75. 4,6-Dinitro-2-methylphenol
534-52-1
25
800
76. N-Nitrosodiphenylamine
86-30-6
10
330
77. 4-Bromophenyl-phenyl ether
101-55-3
10
330
78. Hexachlorobenzene
118-74-1
10
330
79. Pentachlorophenol
87-86-5
25
800
80. Phenanthrene
85-01-8
10
330
81. Anthracene
120-12-7
10
330
82. Carbazole
86-74-8
10
330
83. Di-n-butyl phthalate
84-74-2
10
330
84. Fluoranthene
206-44-0
10
330
85. Pyrene
129-00-0
10
330
86. Butylbenzyl phthalate
85-68-7
10
330
87. 3,3-Dichlorobenzidine
91-94-1
20
660
88. Benz(a)anthracene
56-55-3
10
330
89. Chrysene
218-01-9
10
330
90. bis(2-Ethylhexyl)phthalate
117-81-7
10
330
91. Di-n-octyl phthalate
11 7-84-0
10
330
92. Benzo(b)fluoranthene
205-99-2
10
330
93. Benzo(k)fluoranthene
207-08-9
10
330
94. Benzo(a)pyrene
50-32-8
10
330
95. lndeno(1,2,3-cd)pyrene
193-39-5
10
330
96. Dibenz(a,h)anthracene
53-70-3
10
330
97. Benzo(g,hflperylene
191-24-2
10
330
Specific quantitation limits are highly matrix dependent. The quantitation limits listed herein are provided
for guidance and may not always be achievable.
b Quantitation limits listed for soil/sediment are based on wet weight. The quantitation limits calculated
by the laboratory for soil/sediment on dry weight basis will be higher.
C Medium Soil/Sediment Quantitation Limits (QL) for Semivolatile TCL Compounds are 60 times the
individual Low Soil/Sediment OL.
Based on Contract Laboratory Program Statement of Work, OLMO1 .6 (6/91).
1/96 43 Sample Plan Development
-------
TARGET COMPOUND LIST (TCL) AND
QUANTITATION LIMITS (QL)
Quantitation Limitsb
Water
Low Soil/Sedimentc
Pesticides/PCBs CAS Number (pg/I)
(pg/kg)
98. alpha-BHC 319-84-6 0.05 1.7
99. beta-BHC 319-85-7 0.05 1.7
100. delta-BHC 319-86-8 0.05 1.7
101. gamma-BHC (Lindane) 58-89-9 0.05 1.7
102. Heptachlor 76-44-8 0.05 1.7
103. Aldrin 309-00-2 0.05 1.7
104. Heptachlor epoxide 1024-57-3 0.05 1.7
105. Endosulfan I 959-98-8 0.05 1.7
106. Dieldrin 60-57-1 0.10 3.3
107. 4,4’-DDE 72-55-9 0.10 3.3
108. Endrin 72-20-8 0.10 3.3
109. Endosulfan II 332 13-65-9 0.10 3.3
110. 4,4’-DDD 72-54-8 0.10 3.3
111. Endosulfan sulfate 1031-07-8 0.10 3.3
113. 4,4’-DDT 50-29-3 0.10 33
114. Methoxychlor 72-43-5 0.50 17.0
115. Endrin ketone 53494-70-5 0.10 3.3
116. Endrin aldehyde 7421-36-3 0.10 3.3
117. alpha-Chlordane 5103-71-9 0.5 1.7
118. gamma-Chlordane 5103-74-2 0.5 1 .7
119. Toxaphene 8001-35-2 1.0 170.0
120. Aroclor-1016 12674-11-2 0.5 33.0
121. Aroclor-1221 11104-28-2 0.5 33.0
122. Aroclor-1232 11141-16-5 0.5 67.0
123. Aroclor-1242 53469-21-9 0.5 33.0
124. Aroclor-1248 12672-29-6 0.5 33.0
125. Aroclor-1254 11097-69-1 1.0 33.0
126. Aroclor-1260 11096-82-5 1.0 33.0
Specific quantitation limits are highly matrix dependent. The quantutation limits listed herein are provided
for guidance and may not always be achievable.
b Quantitation limits listed for soil/sediment are based on wet weight The quantitation limits calculated
by the laboratory for soil/sediment on dry weight basis will be higher.
Medium Soil/Sediment Quantutatuon Limits (01) for Pesticides/PCB TCL compounds are 1 5 times the
individual Low Soil/Sediment QL.
Based on the Contract Laboratory Program Statement of Work, OLMO1 .6 16/91)
Sample Plan Development 1/96
-------
INORGANIC TARGET ANALYTE LIST (TAL)
Detection Limit
Analyte (pg/I - water)
Aluminum 200
Antimony 60
Arsenic 10
Barium 200
Beryllium 5
Cadmium 5
Calcium 5000
Chromium 10
Cobalt 50
Copper 25
Iron 100
Lead 3
Magnesium 5000
Manganese 15
Mercury 0.2
Nickel 40
Potassium 5000
Selenium 5
Silver 10
Sodium 5000
Thalliun , 10
Vanadium 50
Zinc 20
Cyanide 10
Sediment detection limit 100 x water (pg/kg - soil/sediment).
Based on the Contract Laboratory Program Statement of Work, ILMO2.1 (9/91).
1/96 45 Sample Plan Development
-------
PB92 - 963356
Publication 9285.7-09A
April 1992
Appendix II
of the
“Guidance for Data Useability in
Risk Assessment (Part”
Final
Office of Emergency and Remedial Response
U.S. Environmental Protection Agency
Washington, D.C. 20460
1/96 47 Sample Plan Development
-------
APPENDIX I I
LISTING OF COMMON POLLUTANTS GENERATED BY SEVEN INDUSTRIES
Appendix H identifies seven industries that generate waste which contains pollutants tha i
are known to pose human and environmental hazards. This appendix is intended to aid the
reader in three ways:
o To assist in the identification of target compounds and potential exposure pathways.
o To predict associated contaminants that potentially yield interferences
o To assist in early identification of sites that contain high levels of compounds that
may not be included as target analytes for routinely available methods
The data for these tables were obtained by searching the USEPA Toxic Release Inventory
System using the Standard Industrial Classification (SiC) codes listed below.
Industry SIC Code
Battery Recycling 3691, 3692
2 Munitions/Explosives 2892
3 Pesticides Manufacturing 2842, 2879
4 Electroplating 3471
5 Wood Preservatives 2491
6 Leather Tanning 3111
7 Petroleum Refining 2911
The appendix consists of seven tables and depicts the pollutants associated with each of
the seven industries, the CAS number of each pollutant, and the matrices where each pollutant
has been found. The list is not inclusive of all pollutants or industrial sources. The seven
industries were selected based on the recommendation of the Risk Assessment Subgroup of the
Data Useability Workgroup because of the frequency of occurrence of the pollutants produced
by those industries in Superfund sites.
Sample Plan Develapment 48 1/96
-------
Appendix!!
LISTING OF COfrIMON POLLUTANTS
GENERATED BY SEVEN INDUSTRIES
INDUSTRY 1: BATFERY RECYCLING
b
Rank Compound CAS Numbcr Air Waxer Soil Othcr
LEAD 7439921 V V V V
2 SODIUM SULFATE (SOLUTION) 7757826 V
3 SODIUM HYDROXIDE (SOLUTiON) 1310732 Y V V
4 SULFURIC ACID 7664939 V V V
5 AMMON IUM SULFATE (SOLUTION) 7783202 V -
6 MANOANESE 7439965 V V V V
7 1 ,l1-TPJCHLOROETHANE 7 1556 V V V
8 METHANOL 67561 V V V
9 FREON 113 16131 V V
10 TR ICHLOROETHYLENE 79016 V V V
11 TOLUENE 108823 V V
12 ZINC 7440666 V V V
13 AMMONIA 7664417 V V V
14 CADMIUM 7440439 V V V V
IS ANTIMONY 7440360 V V V
16 BARIUM 7440393 V y y
17 NICKEL 7440020 V V V V
18 FORMALDEHYDE 50000 V V
a 19 ACETONE 67641 V
20 XYLENE (MIXED ISOMERS) 1330207 V
21 TErRACHLOROETHVLENE 127184 V Y
22. DICHLOROMETRANE 75092 V V
23 PHENOL 108952 V V
24 MERCURY 7439976 Y V V
25 N-BUTYL ALCOHOL 71363 V
26 METHYL ETHYL KETONE 78933 V V
27 METHYLISOBUTYLKETONE 108101 V
28 HYDROCHLORIC ACID 7647010 V V
29 NITRIC ACID 7697372 Y V
30 l,l,I-TRICHLOROETHANE (METHYL CHLOROFORM) 71556 V
31 COBALT 7440484 V V V
32 ARSENIC 7440382 V y
33 COPPER 7440508 y V
34 SILVER 7440224 V Y V
35 ACETOH ITR ILE 75058 y
‘C
Rank = Order of Frequency oiOccurrcrtcc
Other = Other Matrices (Bioca, Hazardous Wa.stc, Sludgc, etc.)
-------
Appendix II
LISTJNG OF COMMON POLLUTANTS
GENERATED BY SEVEN INDUSTRIES
INDUSTRY 2: MUNITIONS/EXpLOSIVES
• b
Rank Compound CAS Numbcr Air Water Soil Other
1 ACETONE 67641 Y y y y
2 NITRIC ACID 7697372 Y Y Y Y
3 AMMONIUM NITRATE (SOLUTION) 6484522 Y Y y y
4 PENTACHLOROPHENOL 87865 y
S SODIUM SULFATE (SOLUTION) 7757826 Y
6 AMMONIA 7664417 Y Y y
7 SULFURIC ACID 7664939 Y y y y
8 METHYL ETHYL KETONE 78933 Y y
9 CYCLOHEXANE 110827 Y y
10 CHLORiNE 7782505 Y y
LI NITROGLYCERIN 55630 y y y y
12 DICHLOROMETHANE 75092 Y y
13 CALCIUM CYANAMIDE 156627 Y y
14 LEAD 7439921 Y y y y
IS ETHYLENE GLYCOL 107211 y y y
16 N-BUTYL ALCOHOL 71363 y
Il TERT-BUTYL ALCOHOL 75650 y
IS M-XYLENE 108383 Y
19 METHANOL 67561 Y y y
20 ASBESTOS (FRIABLE) 1332214 y
21 l,I ,1.TRICHLOROETHANE 71556 y
22 POLYCHLORINATED BIPHENYLS 1336363
23 COPPER 7440508 y y
24 ALUMINUM 7429905 Y y y y
25 2,4-DINITROTOLUENE 121142 Y Y
26 GLYCOL ETHERS 79141 y
27 BENZENE 71432 y y y y
28 BIS(2-ETHYLHEXYL) ADIPATE 103231 y
29 ZINC 7440666 y
30 DIBUTYL PHTHAIATE 84742 y y y
31 SODIUM HYDROXIDE (SOLUTION) 1310732 V y
32 DIETHYL PHTHALATE 84662 y
Rsnk — Ordcr of Frequency of Occurrence
Other Other Maxzsccs (Biota. Hazardous Waste, Sludge. etc.)
-------
Appendix [ I
LISTING OF COM1 1ON POLLUTANTS
GENERATED BY SEVEN INDUSTRIES
INDUSTRY 3: PESTICIDES MANUFACTURING
b
Rftnk Compound CAS Num cr A r W tcr Soil Othcr
SODIUMSULFATE(SOLUT ION) 7757826 y y y
2 AMMONIA 7664417 Y Y y y
3 TOLUENE 108883 Y y y y
4 SODIUM HYDROXIDE (SOLUTION) 1310732 Y y y y
S TITANIUM TETRACHLORIDE 755045’) y
6 METHANOL 67561 Y y y y
7 DICHLOROMETHANE 75092 V y y y
8 XYLENE (MIXED ISOMERS) 1330207 y y y y
9 CHLOROBENZENE 108907 y y y
10 HYDROCHLORIC ACID 7647010 V y y y
11 CHLOROPHENOLS 106489 Y y y y
12 STYRENE 100425 Y Y y
13 ACRYLONITRJLE 107131 Y y y
14 FORMALDEHYDE 50000 Y Y y y
IS CARBON TETRACHLORJDE 56235 Y V y y
16 CHLOROThALOr4IL 1897456 Y y
17 I2-D ICHLOROETHANE 107062 Y V y y
18 ACETONE 67641 Y V y y
19 HEXACHLOROBENZENE 118741 Y Y y
20 1,1J-TRICHLOROETHANE 71556 Y V y
21 ETHYLENEGLYCOL 107211 V Y y y
22 GLYCOL ETHERS 79141 Y Y y y
23 L3-BUTADIENE 106990 Y Y y
24 CHLOROMETHANE 74873 V y
25 CAFTAN 133062 Y y y
26 TETRACHLORO TfjYLENE 127 1S4 Y Y y y
27 CHLORINE 7782505 Y Y y y
28 CARBARYL 63232 V Y y
29 COPPER 7440508 V V y y
30 PARATHION 56382 V Y
31 ZINEB 12122677 y
32 PYRIDINE 110861 Y Y
33 AMMONI(SM NITRATE (SOLUTION) 6484522 Y
34 PHOSPHORIC ACID 7664382 V Y Y y
35 CARBON DISULFIDE 75150 V y
36 1,2,4-TRICHLOROBENZENE 120821 V y y
37 SULFURIC ACID 7664939 V Y y y
38 MALEICANHYDRIDE 108316 V y y
39 ETHYLBENZENE 100414 V Y y
40 2,4-D 94757 V
41 BROMOMETHANE 74839 V
42 SEC-BUTYL . ALCOHOL 78922 V V
Rank - Order of F cqucncy of Occurrence
Other — Other Maxr iccs (Biota, Hazhrdoul Waste, Sludge, etc.)
-------
Appendix [ I
LISTING OF COM1rION POLLUTANTS
GENERATED BY SEVEN INDUSTRIES
INDUSTRY 3: PESTICIDES MANUFACTURING
Rank Compound c Number Air Water Soil Other
43 LEAD 7439921 y
44 CUMENE 98828 y y y
45 M-XYLENE 108383 Y Y
46 ASBESTOS (FRIABLE) 1332214 y y
47 FREON1 I3 76131 Y y
DlCllLOROULNZL I L(M,XLL)I uML S) 25321226 V y y
49 CYCLOHEXANE 110827 Y V Y
50 2,4-DJCHLOROPHENOL 120832 Y Y
$1 I,4-D 1CHLOROBENZENE 106467 Y
$2 D ICHLOROBROMOM E THANE 75274 Y Y
$3 TRIFLU ItAUN 1582098 Y Y Y Y
54 1.2.4-TR IMET}{ YLBEN ZENE 95636 Y Y V
55 METHYLJsOBuTyL roNE 108101 Y Y
56 I,4.DIOX.bJ4E 123911 Y
$7 NITRIC ACID 7691372 Y Y y
58 N-BUTYL ALCOHOL 71363 Y Y Y
59 FLUOMET IjRON 2164172 Y
60 2-METHOXYETHj.j O 109B64 Y
6! B IS(2-ETHYLHEX YL)AD I PATE 103231 Y Y
62 PHENOL 108952 Y Y Y
63 ACRYLiC ACID 79107 Y Y y
64 QUINTOZENE 82688 Y y
65 ALUMINUM 1344281 Y Y V y
66 BENZOYL PEROXIDE 94360 Y Y
67 O-XYLENE 95476 Y
68 CHROMIUM 7440473 Y Y Y
69 2•PHENYLPHENOL 90437 Y Y
70 HYDROGEN CYANIDE 74908 Y Y Y
71 ZINC 7440666 Y Y V Y
72 HEXACHLOROCYCL OpENmD IENE 77474 Y
73 DICOFOL 115322 Y Y
74 B IPHENYL 92524 Y Y y
75 4.N ITROPHENOL 100027 Y y y
76 METHYL ETHYL KETONE 78933 V y
77 TRICI-ILOROETHYLENE 79016 V y
78 M-CRESOL 108394 V V
79 TETRACHLORVINPHOS 961115 y
80 D1(2 - .ETHYLI-{EXYL) PHTI-IALATE (DEHP) 117817 y y
SI TEREPHTHAUC ACID 100210 V y
82 DICHLORVOS 62737 Y y
83 MANEB 12427382 y y
84 P-)(YLENE 106423 V y
Rank Order of Frequency of Occurrence
Other Othcr Matrice.s (Biota, H&mrdous Wasic, Sludge, etc.)
-------
Appendix H
LISTING OF COMMON POLLUTANTS
GENERATED BY SEVEN INDUSTRIES
INDUSTRY 3: PESTJC [ DES MANUFACTURING
Rank Compound CAS Numbcr Air Water Soil O ilier
85 METHYLENE BROMIDE 74953 y
86 CHLORAMBEN 133904 Y Y
87 BENZENE 71432 V Y
88 1- IYDROGEN FLUORIDE 7664393 V V
89 ETHYLENE 74851 V
90 C I . ACID BLUE 9, DJSODIUM SALT 3844459 y
91 DIMETI-’ (L SULFATE 77781 V
92 ISOPROPYL ALCOHOL 61630 V
93 HYDRAZINE 302012 V V
94 VINYL CHLORIDE 75014 V
95 METHYLENEB IS(PHENYL 1SOCVANATE) 101688 V y
96 EP1CHLOROHYDRIN 106898 V
97 PROPYLENE 1 15071 V
98 NITRILOTR IACETIC ACID 119139 y
99 ARSENIC 7440382 V Y
100 NAPHTHALENE 91203 V V
10 ! VINYLIDEF LE CHLORIDE 75354 V
102 TRICKLORFON 52686 ‘i’
103 DIE UTYL PI-ITHALkTE 24742 y
104 ANILINE 62333 V V
105 METHOXYCHLOR 72435 V V y
106 D IETHANOLAMIt4E 111422 V ‘ C y
107 N ITROBENZENE 98953 y y
l o s CYAN IDECOMPOUNDS S il a s
109 p.MMONIU}4 SULFATE (SOLUTION) 77 23202 y
110 L 1 NDANE 58899 y
III POLYCHLORJNATED BIPHENYL,S l336363 y y
112 PROPVLEN OXIDE 7556 ? V
113 2 ,4-DIHFTRJPHENOL 51285 y
1 14 PHOSGENE 15445. y
115 HEXACHLOROETHANE 61721 y
116 CADMIUM 7440439
117 ETHYLENEOXIDE 75218 V
118 BENZYLCHLOR IDE 100447 V y
119 4.6-D!NITRO -O •CRESOL 534521 V
320 CI-ILOROBENZJLATE 510 156 V
‘ C
Rank Order or Frequency of Occurrence
Other = Other Matrices (Bioca. Hazardous Waac, Sludge, etc.)
-------
Appendix H
LISTING OF COMMON POLLUTANTS
GENERATED BY SEVEN INDUSTRIES
INDUSTRY 4: ELECTROPLATING
b
Rank Compound CAS Number Air Water Soil Othcr
I SULFURIC ACID 7664939 V V V y
2 HYDROCHLORIC ACID 7647010 Y V y y
3 SODIUM HYDROXIDE (SOLUTION) 1310732 Y Y y y
4 l.l.I-TR ICHLOROETHANE 71556 Y V y y
S SODIUM SULFATE (SOLUTION) 7757826 V V Y
6 NITRIC ACID 7697372 V V y y
7 DICHLOROMETHANE 75092 y y y
8 NICKEL 7440020 Y y y y
9 TRICHLOROETHYLENE 79016 y y y
10 CHROMIUM 7440473 y y y y
ii TETRACHLOROETHYLENE 127184 Y y y y
12 METHYLETHYLKETONE 78933 Y y y
13 ZINC 7440666 y y y y
14 FREON 113 76131 Y y y
1$ ALUMINUM 7429905 Y y y y
16 COPPER 7440508 Y V y y
17 I’I(OSI’IIORIC ACID 7664382 y y y y
IS TOLUENE 108883 y y y y
19 LEAD 7439921 y y y y
tji 20 XYLENE (MIXED ISOMERS) 1330207 Y y
21 ACETONE 67641 Y y y
22 CADMIUM 7440439 y y y
23 ETHYLBENZENE 100u4 y y
24 ETHYLENEGLYCOL 107211 Y V y y
25 CYANIDE COMPOUNDS 57125 Y y y y
26 AMMONIA 7664417 Y V y
27 FORMALDEHYDE 5 y
28 GLYCOL ETHERS 79141 Y y y
29 CHLORINE 7782505 Y Y y
30 METHANOL 67561 Y y y
31 ETHYLENE OXIDE 75218 Y
32 METHYL ISOBUTYL KETONE 108101 y
33 2-METHOXYETHANOL 109864 y
34 HYDROGEN FLUORIDE 7664393 y y
35 PHENOL 108952 Y y
36 I .2-D ICHLOROBENZENE 95501 Y
37 N-BUTYL ALCOHOL 71363 Y
38 TERT-BUTYL ALCOHOL 75650 y
39 BARIUM 7440393
40 VINYLIDENE CHLORIDE 75354 y
41 2-ETHOXTYETHANOL 110805 Y y
42 ISOPROPYL ALCOHOL 67630 Y
Rank Order of Frequency of Occurrence
Other — Other Matrices (Biola. Hazardous Wazte Sludgc etc.)
-------
Appendix ii
LISTING OF COMMON POLLUTANTS
GENERATED BY SEVEN INDUSTRIES
INDUSTRY 4: ELECTROPLATING
b
Rank Compound CAS Number Air Waic Soil Othcr
43 MANCANI SE 7439965 Y Y
44 HYDROGEN CYANIDE 74908
45 STYRENE 100423 Y
46 TETRACHLORV1NPHOS 961115 Y
47 MELAMINE 108781 V
48 N-DIOCTYLPHTHALATE 117840 y
49 1,4-DIOXANE 1239U Y
50 COBALT 7440484
51 NAPHTRALENE 91203 y
52 AMMONIUM SULFATE (SOLUTION) 7783202 Y
53 SILVER 7440224 V y
54 PROPYLENE 115071 Y
I
Rank Order of Frequency of Occurrence
b
Other Other Mariccs (Biota. Hazudots W&stc. Sludgc. cLc)
-------
Appendix II
LISTING OF COMMON POLLUTANTS
GENERATED BY SEVEN LNDUSTRJES
INDUSTRY 5: WOOD PRESERVATION
Raitk Compound CM Numbc Air Wa
I CHROMIUM 7440473 V Y
2 NAPHTHALENE 91203 V Y
3 AMMONIA 7664417 Y
4 PENTACHLOROpHEN0L 81865 Y Y
5 D IBENZOFURAN 132649 V V
6 ANTHRACENE 120127 V V
7 COPPER 7440508 V Y
8 ARSENIC 7440382 V V
9 FORMALDEHYDE 50000 Y
10 BIPHENYL 92524 Y V
i i BENZENE 71432 Y V
12 D 1CHLOROMETHANE 75092 Y
13 l,1,1-TRICHLOROETHANE 71556 Y
14 AMMONIUM SULFATE (SOLUTION) 7783202 Y
is QUINOLINE 91225 Y V
16 PHENOL 108952 Y V
17 ZINC 7440666 Y y
18 PHOSPHORIC ACID 7664382 Y
19 0-CRESOL 95487 Y V
20 HYDROCHLORIC ACID 7647010 Y
21 M-CRESOL 108394 y y
Rank — Ordcr of Frcqucncy of Occurrcncc
Othcr O hcr Matriccs (Btota. Hazaxdoua Wuze, Siudgc, ctc.)
-------
Appendix II
LISTING OF C(iMMON POLLUTANTS
GENERATED BY SEVEN INDUSTRIES
INDUSTRY 6: LEATHER TANNING
b
Compound CAS Numbcr Air Watc Soil Oihcr
J 4MON1UM SULFATE (SOLUTION) 7783202 Y y y y
2 SULFURIC ACID 7664939 y y y
3 SODIUM HYDROXIDE (SOLUTION) 13l0 y y
4 AMMONiA 7664411 Y y y y
5 TOLUENE 108883 V y
6 SODiUM SULFATE (SOLUTION) 7757826 y
7 METHYL ETHYL KETONE 78933 y y
8 XYLENE (MIXED ISOMERS) 1330207 Y y y
9 CHROMIUM 7440473 Y y y y
10 GLYCOL ETHERS 79141 Y y y
II METHYLISOBUTYLKETONE 108101 V y y
12 2-METHOXYETHANOL 109864 V y y
13 ACETONE 67641 V y Y
14 2-EThOXYETHANOL 110805 y y y
is N-BUTYL ALCOHOL 71363 V y y
16 TETRACHLOROETHYLENE I27184 Y y
17 CYCLOHEXANE 110827 Y y
is AMMONIUMNITRATE(SOLUTION) 6484522 Y
(J 19 MANGANESE 7439965 y y y
20 L1.1-TRJCHLOROETHANE 71556 Y
21 DIC}ILOROMETHANE 75092 Y
22 DIETHANOLAMINE 111422 Y y
23 METHANOL 67561 V
24 ISOPROPYL ALCOHOL 67630 Y Y
25 PHOSPHORIC ACID 7664382 ‘1
26 ETHYLENECLYCOL 107211 Y
27 FREON 113 76131 V
28 PHENOL 108952 y
29 ETHYL ACRYLATE 140985 Y
I
: Order of Frc ucncy of Occurrencc
Othcr Oihcr Mairicci (BioL , Hazazdoui Wa tc S!udgc, ctc.)
-------
Appendix U
LISTING OF COMMON POLLUTANTS
GENERATED BY SEVEN INDUSTREES
INDUSTRY 7: PETROLEUM REFINING
b
Rank Compound CM Number Air Wexcr Soil Other
SODIUM SULFATE (SOLUTION) 7757826 Y Y V Y
2 ALUMINUM 7429905 Y Y y y
3 AMMONIA 7664417 Y y y y
4 SODIUM HYDROXIDE (SOLUTION) 1310732 V Y y y
S SULFURIC ACID 7664939 V Y y y
6 TOLUENE 108883 V V V y
7 XYLENE (MIXED ISOMERS) 1330207 Y Y y y
8 BENZENE 71432 V V V y
9 METHYL ETHYL KETONE 78933 V Y V y
10 PROPYLENE 115071 V Y y
II PHENOL 108952 V Y Y y
12 DIETHANOLAMINE 111422 V Y Y y
13 ETHYLENE
14 METHANOL 61561 Y V V y
15 CYCLOHEXANE 110827 V V Y y
16 I.2 ,4-TRIMETHYLBENZENE 95636 Y V Y Y
17 ET I- IYLBENZEt4E 100414 V Y Y y
IS PHOSPHORIC ACID 7664382 Y Y y y
19 CHROMIUM 7440473 V V V y
20 METHYLTERT-BUTYLETHER 1634044 V Y V y
21 ASBESTOS (FRIABLE) 1332214 V y
22 P-XYLENE 106423 Y Y Y Y
23 AMMONIUM SULFATE (SOLUTION) 7783202 y
24 M-XYLENE 108383 Y Y Y y
25 CUMENE 98828 V V y y
26 ACETONE 67641 Y V V
27 CRESOL (MIXED ISOMERS) 1319773 V V y y
28 HYDROGEN FLUORIDE 7664393 V Y y y
29 O-XYLENE 9 476 V y y y
30 NAPHTHALENE 91203 y y y y
31 NICKEL 7440020 V Y y V
32 CHLORINE 7782505 Y y y
33 LEAD 7439921 V y y y
34 METHYLISOBUTYLKETONE 108101 y
35 ETHYLENEGLYCOL 107211 Y y y y
36 MOLYBDENUM TRIOXIDE 1313275 y y y y
37 ZINC 7440666 y y y y
38 HYDROCHLORIC ACID 7647010 V y
39 CLYCOL ETHERS 79141 y y y y
40 BARIUM 7440393 y V
41 COPPER 7440508 y y y y
42 1.1,1 TR1CFfLOROETHANE 71556 y y y y
Raj k — Order of Frequency ofOccurrencc
Other — Other Meiricci (Biot , Hawdous W ite Sludge, ccc.)
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Appendix II
LISTING OF COMMON POLLUTANTS
GENERATED BY SEVEN INDUSTRIES
INDUSTRY 7: PETROLEUM REFINING
• b
Rank Compound CAS Number Air Water Soil Other
43 ANTiMONY 7440360 Y Y Y V
44 I.3.BIJTADIENE 106990 V Y y
45 N-BUTYLALCOHOL 71363 Y
46 FORMALDEHYDE 50000 Y V y y
47 EP ICHLOROHYDRIN 106298 Y Y
48 COBALT 7440484 Y Y y y
49 VANADIUM (FUME OR DUST) 7440622 Y y y
50 CUMENE HYDROPEROX]DE 80159 V
51 TERT-BUTYL ALCOHOL 75650 V y
52 4.4- ISOPROPYUDENED IPHENOL 80057 V
53 RUTYRALDEHYDE 123728 V
54 BIPHENYL 92524 Y Y y y
55 CARBON TETRACHLORIDE 56235 Y Y y y
$6 STYRENE 100425 Y Y y y
57 TR ICHLOROETHYLENE 79016 V Y
58 MANGANESE 743996S V Y y
59 ETHYLENE OXiDE 75218 y
60 AMMONIUM NITRATE (SOLUTION) 6484522 y
61 CARBON DISULFIDE 75150 Y Y
62 1 2.DICHLOROETHANE 107062 V Y y y
63 POLYCF{LOR 1NATED B1PHENYLS 1336363 y
64 PHOSPHORUS (YELLOW OR WHITE) 7723140 y
65 QUI 14OL 1HE 91225 Y
66 2 .METHOXYETHANOL 109864 y
67 I ,2-DIBROMOETHANE 106934 y y y y
68 TETPACHLOROETHYLENE 127184 Y y y
69 ANTHRACENE 120127 Y Y y
70 2,4-DIMETHYLPHENOL 105679 y y
71 HYDROGEN CYANIDE 74908 V Y
72 CHLOROMETHANE 74873 Y
73 N ITROBENZENE 98953 y
74 I,2-D ICHLOROPROPANE 78875 Y Y y
75 CARBONYL SULFIDE 463581 Y Y
76 ACETONITRILE 75058 Y
77 SILVER 7440254 Y Y y
2. 78 2-ETHOXYETHANOL 110205 V
79 THALLIUM 7440280 Y y
80 FREON 113 76131 V
81 SELENIUM 7782492 V Y y y
82 DICHLOROMEThANE 75092 Y
83 MERCURY 7439976 V V V
84 CADMIUM 7440439 Y y y
Rank - Order of Frequency of Occurrenco
Other — Other Maxrices (Biota. Hazardouu Wadc Sludge. etc.)
‘.3
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Aupendix II
LISTING OF CdMMON POLLUTANTS
GENERATED BY SEVEN iNDUSTRIES
INDUSTRY 7: PETROLEUM REFINING
b
Ran k Compound CAS Numb.r Air Water Soil Other
25 I.L2-TRICHLOROETHANE 79005 Y Y
86 ARSENIC 7440382 Y Y V ‘1
87 CYANIDE COMPOUNDS $712.5 Y
88 CHLORINE DIOXIDE 10049044 Y
89 ACRYLIC ACID 79107 Y
90 I .3-DICIILOROPROPYLENS 542756 Y
91 I .2-BUTYLENE OXIDE 106387 Y
92 CHLOROBENZENE 108907 Y
93 1 ,4-DIOXANE 123911 Y
94 DI(2 -ETHYLHEXYL) PHTHALATE (DEHP) I 17317 V
95 BERYLLIUM 7440417 Y
96 CHLOROFORM 67663 Y
0\
Rank — Order of Frequency of Occurrcncc
Othcr — Other Matrices (Biota, Hazardous WagD , Sludge, ac.)
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REFERENCES
U.S. EPA. 1989. Methods for Evaluating the Attainment of Cleanup Standards: Volume 1—Soil
and Solid Media. EPA 230/02-89-042. U.S. Environmental Protection Agency, Washington, DC.
U.S. EPA. 1991a. Compendium of ERT Groundwater Sampling Procedures. EPA/P-91/007. U.S.
Environmental Protection Agency, Washington, DC.
U.S. EPA. 1991b. Compendium of ERT Soil Sampling and Surface Geophysics. EPA/540/P-
91/006. U.S. Environmental Protection Agency, Washington, DC.
U.S. EPA. 1991c. Compendium of ERT Surface Water and Sediment Sampling Procedures.
EPA/540/P-91/005. U.S. Environmental Protection Agency, Washington, DC.
U.S. EPA. 1991d. Compendium of ERT Waste Sampling Procedures. EPAI54O/P-91-008. U.S.
Environmental Protection Agency, Washington, DC.
U.S. EPA. 1991e. Removal Program Representative Sampling Guidance: Volume 1—Soil. Reprint
of OSWER Directive 9360.4-10. PB92-963408. U.S. Environmental Protection Agency,
Washington, DC.
U.S. EPA. 1992a. Guidance for Data Useability in Risk Assessment (Part A). PB92-963356. U.S.
Environmental Protection Agency, Washington, DC.
U.S. EPA. 1992b. QASPER Fact Sheet. U.S. Environmental Protection Agency, Office of Solid
Waste and Emergency Response, Washington, DC.
U.S. EPA. 1993. Data Quality Objectives Process for Superfund. EPA-540-R-93-071. U.S.
Environmental Protection Agency, Washington, DC.
1/96 61 Sample Plan Development
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United States
Environmental Protection
Agency
Superfund
Office of
Solid Waste and
Emergency Response
Publication 9355.9-01
EPA54 O-R-93-071
P894-963203
September 1993
EPA
DATA QUALITY OBJECTIVES
PROCESS FOR SUPERFUND
Interim Final Guidance
w ww
w w w
ir — - i--- -T .
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9355.9-01
EPA54O-R-93-071
P B94-963203
September 1993
DATA QUALITY
OBJECTIVES PROCESS
FOR SUPERFUND
Interim Final Guidance
Office of Emergency and Remedial Response
U.S. Environmental Protection Agency
Washington, DC 20460
Pnnted on Recycled Paper
-------
NOTICE
The procedures set forth in this document are intended as
guidance to employees of the United States Environmental
Protection Agency (EPA) and other government agencies.
These guidelines do not constitute EPA rulemaking and cannot
be relied upon to create any substantive or procedural rights
enforceable by any party in litigation with the United States.
EPA reserves the right to act at variance with the policies and
procedures in this guidance, based on analysis of site-specific
circumstances. EPA also reserves the right to modify this
guidance at any time without public notice.
U
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TABLE OF CONTENTS
Page
LIST OF FIGURES V
IIS’l’ OF ‘I’A.BLES V
FOR_E%S’OR.D . vii
LIS’rOFACRON’tMS viii
INTRODUCTION 1
OVERVIEW AND PURPOSE OF THIS DOCUMENT I
BENEFITS OF THE DQO PROCESS 4
THE DQO PROCESS AND STATISTICS 4
IMPLEMENTING THE DQO PROCESS 5
HOW THE DQO PROCESS FITS INTO INTEGRATED SITE
ASSESSMENT/SACM 6
WHERE TO FIND MORE INFORMATION ABOUT THE DQO PROCESS 7
CHAPTER1. STEP1: STATETHEPROBLEM 9
1.1 BACKGROUND 9
1.2 ACTIVITIES 10
1.3 OUTPUTS 12
CHAPTER 2. STEP 2: IDENTIFY THE DECISION 13
2.1 BACKGROUND 13
2.2 ACTIVITIES 14
2.3 OUTPUTS 15
CHAPTER 3. STEP 3: IDENTIFY THE INPUTS TO THE DECISION... 17
3.1 BACKGROUND 17
3.2 ACTIVITIES 18
3.3 OUTPUTS 19
CHAPTER 4. STEP 4: DEFINE TILE BOUNDARIES OF THE STUDY .. 21
4.1 BACKGROUND 21
4.2 ACTIVITIES 22
4.3 OUTPUTS 25
111
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TABLE OF CONTENTS. CONTINUED
Page
CHAPTER 5. STEP 5: DEVELOP A DECISION RULE 27
5.1 BACKGROUND 27
5.2 ACTIVITIES 27
5.3 OUTPUTS 28
CHAPTER 6. STEP 6: SPECIFY LIMITS ON DECISION ERRORS 29
6.1 BACKGROUND 29
6.2 ACTIVITIES 31
6.3 OUTPUTS 34
CHAPTER 7. STEP 7: OPTIMIZE THE DESIGN 37
7.1 BACKGROUND 37
7.2 ACTIVITIES 38
7.3 OUTPUTS 42
7.4 SUPERFITND DATA CATEGORIES 42
CHAPTER8. STEPS: BEYONDTFLEDQOPROCESS . 45
8.1 OVERVIEW 45
8.2 SAMPLING AND ANALYSIS PLAN DEVELOPMENT 46
8.3 DATA QUALITY ASSESSMENT 47
APPENDICES
I TECHNICAL SUPPLEMENT TO THE DATA QUALITY OBJECTIVES PROCESS ... 49
I I APPLICATION OF DATA QUALITY OBJECTIVES TO SUPERFUND siTEs
(EXAMPLES) 81
Section A: Ground-water Example 81
Section B: Removal Program Example 93
Section C: Remedial Program Example 103
LU GLOSSARY 111
IV BIBLIOGRAPHY 115
iv
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Figure 1.
Figure 2.
Figure 3.
Figure 4-1.
Figure 6-1.
Figure 7-1.
Figure 8-1.
Figure 8-2.
LIST OF FIGURES
Page
2
3
6
23
35
36
41
46
47
LIST OF TABLES
Decision Error Limits Table Corresponding to Figure 6-1
Decision Error Limits Table Corresponding to Figure 6-2
The Data Quality Objectives Process
QA Planning for Superfund Data Collection
Repeated Application of the DQO Process
Defining Spatial Boundanes
An Example of a Design Performance Goal
Parameter Exceeds Action Level
Figure 6-2. An Example of a Design Performance Goad
Parameter is Less Than Action Level .
An Example of a Power Curve
QA Planning and the Data Life Cycle
The Data Quality Assessment Process
Diagram - Baseline Condition:
Diagram - Baseline Condition:
Table 6-1.
Table 6-2.
35
36
V
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FOREWORD
The U.S. Environmental Protection Agency (EPA) undertakes cleanup activities at abandoned
hazardous waste sites under the Comprehensive Environmental Response, Compensation, and Liability
Act (CERCLA), also known as the Superfund program. Many of the activities involve the collection
and evaluation of site-specific environmental data EPA has developed and implemented a mandatory
Agency-wide program of quality assurance for environmental data, mcluding a process for developing
Data Quality Objectives (DQOs), as an important tool for project managers and planners to determine
the type, quantity, and quality of data needed to make defensible decisions.
The Office of Emergency and Remedial Response (OERR) is promoting a common
understanding of the quality assurance requirements for site-specific data collection activities. The
DQO Process is an effective means by which managers and technical staff can implement the
mandatory Superfund quality assurance requirements. The Agency has developed this guidance on
Data Quality Objectives Process for Superfund to replace the earlier guidance, Data Quality Objectives
for Remedial Response Activities (EPA 5401G-87/003, OSWER Directive 9355.O-7B) and the five
analytical levels introduced in that document.
It is the goal of the Superfund program and the regulated community to collect data of
appropnate quality for environmental decisions while minimizing expenditures related to data
collection by eliminating unnecessary duphcation or unnecessarily detailed data. The most effective
way to accomplish this is to implement the DQO Process.
C SZAJ 4 ft &
f LHenry L. Longest H, Director
Office of Emergency and Remedial Response
Bmc o r
Office of aste Programs Enforcement
vii
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LIST OF ACRONYMS
ARAR Applicable or Relevant and Appropriate Requirement
CERCLA Comprehensive Environmental Response, Compensation, and Liability Act
CFR Code of Federal Regulations
DQO or DQOs Data Quality Objectives
EEJCA Engineering Evaluation and Cost Analysis
ESI Expanded Site Investigation
EU Exposure Unit
FS Feasibility Study
HRS Hazard Ranking System
MCL Ma,imum Contaminant Level
NCP National Oil and Hazardous Substances Pollution Contingency Plan
NPL National Priorities List
OSC On-Scene Coordinator
OSWER Office of Solid Waste and Emergency Response
PA Preliminary Assessment
PRG Preliminary Remediation Goal
PRP Potentially Responsible Party
QAPP Quality Assurance Project Plan
RD Remedial Design
RDT Regional Decision Team
RI Remedial Investigation
RI’ 4E Reasonable Maximum Exposure
RPM Regional Project Manager
RU Remediation Unit
SACM Superfund Accelerated Cleanup Model
SAM Site Assessment Manager
SEA Site Evaluation Accomplished
SI Site Inspection
viii
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INTRODUCTION
OVERVIEW AND PURPOSE OF THIS DOCUMENT
This document provides guidance on developing Data Quality Objectives (DQOs) for
Superfund sites. This guidance replaces EPA/5401G-871003, Data Quality Objectives for Remedial
Response Activities: Development Process.
Each year the U.S. Environmental Protection Agency (EPA) and the regulated community
spend approximately $5 billion collecting environmental data for scientific research, regulatory
decision making, and regulatory compliance. While these activities are necessary for effective
environmental protection, it is the goal of EPA and the regulated community to minimize expenditures
related to data collection by eliminating unnecessary, duplicative, or overly precise data. At the same
time, they would like to collect data of sufficient quantity and quality to support defensible decision
making. The most efficient way to accomplish both of these goals is to begin by ascertaining the
type, quality, and quantity of data necessary to address the problem before the study begins.
What Is the DQO Process? The DQO Process is a series of planning steps based on the Scientific
Method that is designed to ensure that the type, quantity, and quality of environmental data used in
decision making are appropriate for the intended application. The steps of the DQO Process are
illustrated in Figure 1.
What are DQOs? DQOs are qualitative and quantitative statements derived from the outputs of each
step of the DQO Process that:
1) Clarify the study objective;
2) Define the most appropriate type of data to collect;
3) Determine the most appropriate conditions from which to collect the data; and
4) Specify acceptable levels of decision errors that will be used as the basis for
establishing the quantity and quality of data needed to support the decision.
The DQOs are then used to develop a scientific and resource-effective sampling design.
The DQO Process was developed by EPA to help Agency personnel collect data that are
important to decision making. The process allows decision makers to define their data requirements
and acceptable levels of decision errors’ during planning, before any data are collected. Application
of the DQO Process should result in data collection designs that will yield results of appropriate
quality for defensible decision making.
Why was this document developed for Superfund? Mandatory quality assurance (QA) requirements
for EPA environmental data collection activities are established in EPA Order 5360.1, Policy and
Pro gram Requirements to Implement the Quality Assurance Program. Additionally, the National Oil
and Hazardous Substances Pollution Contingency Plan (NCP; 40 CFR Part 300) mandates specific
Superfund QA requirements. Both documents emphasize that Superfund environmental data must be
of known quality and require the development of Quality Assurance Project Plans (QAPPs) for all
environmental data collection activities to achieve this goal. The NCP mandates the development of a
‘Decision errors occur when variability or bias in data mislead the decision maker into choosing an incorrect course of
action. Decision crrors arc discussed in detail in Chapter 6: SPECIFY LIMITS ON DECISION ERRORS.
1
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1. State the Problem
Summarize the contamination problem that w lI require new environmental
data, and identify the resources available to resolve the problem.
4
2. Identify the Decision
Identity the decision that requires new environmental
data to address the contamination problem.
4
3. Identify Inputs to the Decision
Identify the Information needed to support the decision, and
specify which inputs require new environmental measurements.
4. Define the Study Boundaries
Specify the spatial and temporal aspects of the environmental
media that the data must represent to support the decision.
4
5. Develop a Decision Rule
Develop a logical if... then... statement that deflnes the conditions that
would cause the decision maker to choose among alternative actions.
6. Specify Limits on Decision Errors
Specify the decision makeras acceptable limits on decision errors, which are
used to establish performance goals for limiting uncertainly in the data.
7. Optimize the Design for Obtaining Data
Identify the most resource-effective sampling and analysis design
for generating data that are expected to satisfy the DOOs.
Figure 1. The Data Quality Objectives Process
2
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Sampling and Analysis Plan (SAP), which
specifies acceptable data quality goals, defines
responsibility for achieving these goals, and
includes as its key elements a field sampling
plan and a QAPP. Figure 2 illustrates the
elements of QA planning for Superfund.
The DQO Process requires site managers
to specify acceptable data quality goals by
establishing acceptable limits on decision errors.
The DQO Process outputs, including the
acceptable limits on decision errors, provide the
information necessary to develop the SAP. The
DQO Process and the SAP requirements satisfy
EPA Order 5360.1 and the NCP’s mandate. This
guidance document revises the Superfund
program’s approach to developing DQOs to be
consistent with the following Agency-wide QA
requirements and guidance documents:
EPA Quality System Requirements for
Environmental Pro granis. EPAJQA/R- 1.
1993.
Interim Draft EPA Requirements for Quality Figure 2. QA Planning for
Management Plans. EPA/QA/R-2. Superfund Data Collection
1992.
EPA Requirements for Quality Assurance Project Plans for Environmental Data Operations.
EPAJQAJR-5. 1993.
Guidance for Planning for Data Collection in Support of Environmental Decision Making Using the
Data Quality Objectives Process. EPA/QAJG-4. 1993.
Guidance for Conducting Environmental Data Quality Assessments. EPAJQA/G-9. 1993.
How Is this document organized? This document is organized as follows: Chapters 1 through 7
describe procedures for implementing the DQO Process at Superfund sites. Each of these chapters
describes a step of the DQO Process, and includes a background section that explains the purpose of
that step, activities for developing the outputs of that step, and a list of expected outputs. Chapter 8
discusses the relationships between the DQO Process, the Sampling and Analysis Plan, and Data
Quality Assessment.
This guidance is supported by several appendices. Appendix I describes in more detail
selected topics relating to DQO development activities. Appendix II provides three examples of DQO
development: a pre-remedial program (site inspection) ground-water example, a removal program soil
example, and a remedial program soil example. Appendix ifi contains a glossary of terms used in this
guidance document, and Appendix IV contains a bibliography of documents used in the development
of this guidance.
SINGLE
INTEGRATED
DOCUMENT
3
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BENEFLTS OF THE DQO PROCESS
The DQO Process is a planning tool to help site managers decide what type, quality, and
quantity of data will be sufficient for environmental decision making. The outputs of the DQO
Process can be used to develop a statistical sampling design and to effectively plan field investigations
that can stand up to rigorous review.
By using the DQO Process, a site manager provides criteria for determining when data are
sufficient for site decisions. This provides a stopping rule a way for site managers to determine
when they have collected enough data. In addition, the DQO Process:
Improves Sampling • helps site managers streamline field investigations and decide how many
and Analysis Designs samples and analyses are required to support defensible decision making;
• helps site managers define where and when samples should be collected;
• provides the QA community with a scientific basis for defining the right
type arid number of quality control and quality assessment samples and
associated analytical precision and recovery requirements;
Saves Money and Time ‘ helps field personnel identify resource-efficient sample collection
methods,
• helps laboratory analysts identify resource-effective analytical methods;
• can drastically reduce overall project costs by improving the quality of
information for decision making (for example, defining areas of the site
that require remediation) arid by eliminating expensive rework;
Improves Decision • helps site managers develop a statistical sampling design that controls
Making decision erron.
• provides a sirucrure (or clarifying multiple study objectives into specific
decisions,
• encourages the pazlicipation and communication of data users and
relevant technical e pens in planning, implementation, and assessment.
The DQO Process is based on the icientific method, and therefore improves the legal
defensibility of site decisions by providing a complete record of the decision process and criteria for
arriving at conclusions.
It is important to remember that there is a tradeoff between the desire to limit decision errors
and the cost of reducing decision eriors. Reducing decision errors can be costly because more samples
and more analyses are often required. One of the goals of the DQO Process is to help decision makers
strike the best balance between acceptable limits on decision errors and the cost of meeting those
decision error limits.
THE DQO PROCESS AND STATISTICS
The DQO Process has both a quantitative and a qualitative aspect. The quantitative aspect
seeks to use statistics to design the most efficient field investigation that controls the possibility of
making an incorrect decision. The qualitative aspect seeks to encourage good planning for field
investigations and complements the statistical design. Users of this guidance are encouraged to pursue
both aspects of the DQO Process. A field investigation can always benefit from good planning, even
if planning does not lead to a statistical design.
4
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Generally, the quantitative aspect and subsequent statistical design ate important when site
contaminant levels are close to an action level, or when variability in the data is so great that the
results are inconclusive. In such cases, a it.atistical design can provide quantitative estimates of the
level of uncertainty in the data and, therefore, help the decision maker understand and control the
probability of making an incorrect decision based on the data.
The statistical procedures used in the DQO Process provide:
a scientific basis for making inferences about a site (or a portion of a site) based on
information contained in environmental samples;
• a basis for defining data quality criteria and assessing the achieved data quality for
supporting integrated site assessment decisions;
• a foundation for defining meaningful quality control procedures that are based on the
intended use of the data;
• quantitative criteria for knowing when site managers should stop sampling (i.e., when the
site has been adequately characterized); and
• a solid foundation for planning subsequent data collection activities.
Non-probabilistic or subjective (judgmental) sampling approaches can be useful and
appropriate for satisfying certain field investigation (study) objectives. For instance, if the study
objective is to locate and identify potential sources of contamination, a subjective identification of
sampling locations may be the most efficient method to employ. 2 If the objective is to establish that a
threat exists in a complete exposure pathway by confirming the presence of a hazardous substance
associated with the site or process, a judgmental sampling approach can be used. However, because of
the subjective nature of the selection process, data generated from non-probabilistic samples should not
be used if the goal of the study is to characterize some property of the site as a whole.
IMPLEMENTING THE DQO PROCESS
The scoping team should follow each step of the DQO Process for each medium of concern.
Once the scoping team has gone through the process completely for one medium, it becomes easier
and quicker to develop additional sets of DQOs in other media. For example, typically at Superfund
sites the contaminants of concern identified in the early assessment phase remain the focus of
subsequent field investigations in the advanced assessment, even though the decision and the action
level may change. Similarly, the areas of concern that are directly related to the geographical
boundaries of the study usually do not vary much through the site assessment process. Therefore,
much of the DQO outputs generated in the early assessment will be applicable in advanced assessment
planning.
The DQO Process is flexible and iterative. Often, especially for more complicated sites, the
scoping team will need to return to earlier steps to rethink or better focus the output. These iterations
through the earlier steps of the DQO Process can lead to a more focused design that can save
resources in later field investigation activities.
2 An important caveat here is that if contamination is not found, then without a statistical approach very little can be said
about the probability of having missed the source of contamination.
5
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The DQO Process should be used repeatedly during the life cycle of a project. Early in the
project, a more preliminary and qualitative application of the DQO Process may be appropriate to meet
the site manager’s needs. As more details arid decisions about the site develop, a more thorough and
quantitative application of the DQO Process usually is warranted. Figure 3 illustrates this point
graphically. During early assessment, a site manager may decide to apply only the more qualitative
aspects of the DQO Process, rely less on the quantitative aspect, and not use a statistical sampling
design, especially since this is not a decision that requires a full assessment of health or environmental
risks. In the advanced assessment phase, the possibility that uncertainty in environmental data may
lead to incorrect decisions becomes more critical and a site manager may place more emphasis on the
quantitative aspects of DQO development.
Figure 3. Repeated Application of the DQO Process
HOW THE DQO PROCESS FITS INTO INTEGRATED SITE ASSESSMENTISACM
The DQO Process provides a logical framework for planning multiple field investigations,
thereby fulfilling the integrated site assessment goal of cross-program response planning and allowing
optimal cross-program data useability. By emphasizing the need to place limits on the probability of
taking incorrect actions, the DQO Process complements the integrated site assessment objective of
evaluating the need for action. The DQO Process places a worthwhile investment on planning, which
results in timely and efficient cleanups, thereby increasing the chances of taking the correct action.
For these reasons, the DQO Process is an effective approach for accomplishing and satisfying the goals
of the Superfund Accelerated Cleanup Model (SACM). This guidance document is the primary
document for planning site assessment field investigations. However, users should consult other
relevant Superfund guidance that provide more detailed information on specific site assessment
activities. Appropriate references are included throughout this guidance, and Appendix IV provides a
summary of references organized by DQO topic.
000,
£ 6 LU47
rr!AAI1
U
INCREASING LEVEL OF EVALUATION EFFORT
6
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WHERE TO FIND MORE INFORMATION ABOUT THE DQO PROCESS
A DQO training course is available through the EPA Training Institute at U.S. EPA
Headquarters in Washington, D.C.
Additional documents on DQO applications can be obtained from the Quality Assurance
Management Staff at EPA Headquarters.
EPA regional and national program office quality assurance managers can provide assistance in
learning more about the DQO Process.
7
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CHAPTER 1
STEP 1: STATE THE PROBLEM
THE DATA QUALITY OBJECTIVES PROCESS
\ fyt Decision
Identify tnput” ,Decision I
If
N
N
Optimize the Design for Obtaining Data
1.1 BACKGROUND
The purpose of this step is to
• establish the DQO scoping team;
• provide a brief descnption of the contamination problem that presents a potential
threat/unacceptable nsk to human health and the environment; and
• identify resources available to address the problem.
Stating the problem typically involves a description of the source and/or location of
contamination including physical and chemical factors associated with the site that could result in
contaminant release or unacceptable exposures. The description should include the regulatory and
programmatic context of the problem, such as the regulatory objectives and basis for the field
investigation. The description of the potential contamination problem should also include appropriate
action levels for evaluating and responding to releases or exposures, and appropriate response actions.
I
late the Problem
Define the Study Boun 4
1
I
STATE THE PROBLEM
Puipose
Summarize the contamination problem thai wifl
require new environmental data, and identify
the resoumes avaiable to resolve the
problem.
Activities
• identity members of the scoping learn.
• Develop/refine the conceptual site modeL
o Define the exposure scenarios.
• Specdy available resources.
• Write a brief summary of the contamination
problem.
Develop a Decision Rule
‘I ,
Specify Limits on Decisron Errors
9
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The scoping team is a multidisciplinary group of experts. They develop or refine a conceptual
site model that describes and illustrates the known and suspected sources of contamination, potential
migration pathways, and potential human and environmental receptors. The scopirig team begins by
collecting and evaluating all historical site data to formulate the conceptual site model and assess the
extent to which the available historical site data support exposure scenarios that are developed later in
the site assessment process. These descriptions aid in understanding the relationship among potential
contaminant releases, sources of contamination, and physical and environmental targets.
1.2 ACTIVITIES
Identify Members of the Scoping Team
The creation of the scoping team is a two-step process. The first step is to identify the
decision maker for the site. The decision maker (usually the site manager) and his technical staff
identify the other members of the scoping team based on a preliminary understanding of the nature of
the contamination problem (e.g., potentially affected media). The site manager’ delegates
responsibility for accomplishing planning tasks to the other members of the scoping team. However,
the site manager makes the final decisions at the site.
The second step is to choose the members of the scopi.ng team. The team should include
representatives who are knowledgeable about several project phases, including QA specialists,
samplers, chemists, modelers, technical project managers, human health and ecological risk assessors,
toxicologists, biologists, ecologists, administrative and executive managers, data users, Natural
Resource Trustees, and a statistician (or someone knowledgeable and experienced with environmental
statistical design).
Every member of the scoping team will support or actively participate in all steps of the DQO
Process. Their roles will include interpreting historical site data and preparing their team members for
accomplishing DQO activities. They will also attend meetings to help generate DQO outputs that will
guide the field investigation data collection designs.
Develop/Refine the Conceptual Site Model
Collect all available historical site data 1 including QA/QC documentation associated with
previous environmental data collection activities. Use the information to develop a diagram that
illustrates the relationships between:
• locations where contamination exists or contaminant/waste sources,
• types and concentrations of contaminants,
• potentially contaminated media, migration pathways,
• potential physical and environmental targets or receptors.
Presenting historical site data in this manner provides a foundation for identifying data gaps and
focusing on where the problems of potentially unacceptable contamination may or may not exist.
More information on developing the conceptual site model (CSM) can be found in Appendix I,
Section A. For more extensive information sources, refer to the Guidance for Pe fornzjng Site
Inspections Under CERCL4, and the Guidance for Conducting Remedial Investigation and Feasibility
Studies Under CERCLA.
‘Throughout this document, the Site manager is assumed to be the decision maker.
10
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Define Exposure Pathways and Exposure Scenarios
The goal of this step is to define site conditions that indicate or could lead to an unacceptable
threat or exposure at the site. Use the conceptual site model and relevant information on migration
pathways as a base for accompllshLng this task. For the early phases of site assessment activities, it is
necessary to establish that a complete exposure pathway exists. In general, identify currently
contaminated media to which individuals or sensitive ecosystems may be exposed. Following
identification of the media of concern, identify potential contaminants of concern based on historical
site use, analytical data, or anecdotal information. Next. defme the current and future land use.
Following this, determine the local/state applicable or relevant and appropriate requirements (ARARs)
for the site. For cases where multiple contaminants exist and A.RARs are not available for all the
contaminants, develop risk-based contaminant-specific preliminary remediation goals (PRGs).
Chemical-specific PRGs are concentrations based on ARARs or concentrations based on risk
assessment. PRGs should also be developed even when ARARs are available for all contaminants arid
meeting all ARARs is not considered protective. For each medium and land use combination, identify
complete exposure pathways and assemble all this information into exposure scenarios that are
expected to represent the highest exposure that could reasonably occur at the site. More detailed
information on accomplishing the above activities during scoping can be found in the Risk Assessment
Guidance for Superfund: Volume 1 - Human Health Evaluation Manual (Part B. Development of Risk-
based Preliminary Remediation Goals), EPA/54OfR-92J004.
It is efficient to evaluate the potential for an unacceptable ecological threat during the human
health evaluation. The following text discusses important relationships between human health and
environmental evaluations:
Environmental evaluation and human health evaluation are parallel activities in the
evaluation of hazardous waste sites. Much of the data and analyses relating to the
nature, fate, and transport of a site’s contaminants will be used for both evaluations.
At each point of these common stages, however, analysts should be sensitive to the
possibility that certain contaminants and exposure pathways may be more important for
the environmental evaluation than for the health evaluation, or vice versa. It is also
important to recognize that each of the two evaluations can sometimes make use of the
other’s information. For example, the potential of a contaminant to bioaccumulate
may be estimated for a health evaluation but be useful for the environmental
evaluation. Similarly, measurement of contaminant levels in sport and commercial
species for an environmental evaluation may yield useful information for the health
evaluation. 2
For additional information on Exposure Assessment issues and ARARs refer to the Risk
Assessment Guidance for Superfiind Volume 1-Human Health Evaluation Manual, Part A and Part B;
Risk Assessment Guidance for Supe,fun4 Volume 11-Environmental Evaluation Manual; Framework
for Ecological Risk Assessment; EPA Risk Assessment Forum (Feb. 1992); A Review of Ecological
Assessment Case Studies from A Risk Assessment Perspective; EPA Risk Assessment Forum
(May, 1993); CERCL4 Compliance with Other Laws Manual; and Guidance for Data Useabiliry in
Risk Assessment (Part A).
2 Rtsk Asseismem Guidance for Superfluid, Volume II - Environmental Evaluation Manual. p. 3.
11
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Specify the Available Resources
(1) Define the budget. Specify the approximate monetary budget for the field investigation.
This estimate should account for developing DQOs and for carrying out the potential
sampling and analysis activity under consideration.
(2) Define the time constraints. Determine the time constraints, such as the Superfund
recommended time frame, for completing the various required site evaluations. Other
factors to consider include political factors such as public concern and the timeliness of
addressing health and ecological risks.
Write a Brief Summary of the Contamination Problem
Summarize relevant background into a concise description of the problem to be resolved.
1.3 OUTPUTS
The main output of this step is a complete description of the contamination problem that
includes the regulatory and programmatic context of the problem. This description typically consists
of:
a list of the known and suspected contaminants in each medium and estimates of their
concentration, variability, distribution, and location;
• the conceptual site model and exposure pathways;
• a summary of the outcome and status of any previous response(s) at the site, such as early
actions or previous data collection activities;
• the site’s physical and chemical characteristics that influence migration and associated
human, environmental, and physical target(s); and
• an estimate of the budget, schedule, and available personnel necessary to implement the
appropriate response for the site.
12
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CHAPTER 2
STEP 2: IDENTIFY THE DECISION
THE DATA QUALITY OBJECTIVES PROCESS
IDENTIFY THE DECISION
Purpose
Identity the decision that requires new
enviionmental data to address me
contamination poblem.
ActMtles
• Identify the key decision for the current
phase or stage oZ the pro e .
• Identity alternative adlons that may be
taken based on the findings of the field
inves ga11on.
• identity relationships between this
decision and any other current or
subsequent decisions.
Optimize the Design for Obtaining Data
2.1 BACKGROUND
The purpose of this step is to identify the decision that will use environmental data to address
the potential contamination problem and to state the actions that could result from the resolution of
each decision statement. This is how the scoping team defines the objective of the field investigation.
Generally, environmental field investigations may be designed to satisfy a broad array of
objectives, such as demonstration of regulatory compliance, research, monitoring for trends, or
estimation of average characteristics. For Superfund, however, most field investigations are designed
to support the site manager’s selection of appropriate response actions (te., recommend the Site
Evaluation Accomplished (SEA) or further assessment or even a removal/remedial response action).
Since the field investigation objective can be viewed as a choice between alternative actions, this
document describes the objectives as being synonymous with the decision and associated actions. This
chapter presents four major site assessment decisions and associated actions. The site assessment
decisions and associated actions listed below address the most important Removal and Remedial data
collection activities. Site managers who are addressing at least one of these major site assessment
decisions should proceed directly to that section below and identify the decision and corresponding
actions. For site managers who are not addressing one of the major decisions, this guidance provides
activities to help develop project-specific decision statements below.
State the Problem
It
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Stating the decision will help focus the efforts of the scoping team toward a common
objective. The actions taken will be based on the outcome of the field investigations and will lay the
foundation for defining the data quality requirements. The decision statement and alternative actions
together provide an initial confirmation of the assumption that environmental data are needed to help
resolve the potential contamination problem.
2.2 ACTIVITIES
Identify the Key Decision for the Current Phase or Stage of the Project
Review the list of decisions presented below and select the appropriate decision for the current
phase of the site assessment process.
EARLY ASSESSMENT DECISION
Determine whether the release poses a potential threat to human health or the environment.
ADVANCED ASSESSMENT DECISION, PHASE I
Determine whether the concentration of contaminants of concern exceed ARARs or exceed
contaminant concentrations corresponding to the preliminary remediation goal for the site.
ADVANCED ASSESSMENT DECISION, PHASE El
(EXTENT OF CONTAMINATION)
Determine the volume of media that exceeds action level(s) (i.e., ARARs, concentrations
corresponding to the preliminary remediation goal, removal action levels, or final
remediation levels).
CLEANUP ATTAINMENT DECISION
Determine whether the final remediation level(s) or removal action level(s) have been
achieved.
If a decision other than one from the list above will be addressed, perform the following
activities:
(1) Consider the actions that EPA, the potentially responsible parties, or another collective
group will take based on the outcome of the field investigation. For example, what will be
done to resolve the potential contamination problem? Is it necessary to collect data on
contaminant concentrations in order to decide if the site-related contamination exceeds
regulatory standards, including ecological screening levels?
(2) Examine the regulatory objectives for this phase of the remedial process. For example,
when a site is listed on the National Priorities List (NPL), but a baseline risk assessment
has not been conducted, then the regulatory objective is to determine the nature and
magnitude of contamination.
(3) Perform a consistency check by assessing whether the decision will be responsive to the
potential contamination problem.
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Identify Alternative ActIons that May Be Taken Based on the Findings of the Field Investigation
Select the actions that will be taken based on the outcome of the field investigation that
correspond with the selected decision above.
Actions based on early assessment decision
(I) Recommend the site evaluation accomplished (SEA) response for the site; or
(ii) Recommend that the site warrants consideration of further assessment or a possible
response action.
Actions based on advanced assessment decision, Phase I
(i) Recommend the SEA response for the site; or
(ii) Recommend that the site warrants consideration of further assessment or a possible
response action.
Actions based on advanced assessment decision, Phase II
(i) Designate the area/volume for remediation; or
(ii) Do not designate the area/volume for remediation.
Actions based on cleanup attainment decision
(I) Recommend the SEA response and proceed with delisting procedures; or
(ii) Recommend that further response is appropriate for the site.
Confirm that the actions associated with the list of decisions above will help to resolve the
contamination problem by determining if actions are consistent with and satisfy regulatory objectives.
Also, based on the statement of the problem and decision, assess if the range of actions helps to
achieve the goal of protecting human health and the environment.
Identify Relationships Between This Decision and Any Other Current or Subsequent Decisions
If several decisions will be made, identify each decision and establish the relationship among
them and their order of priority. Then, identify the actions that are associated with each decision and
determine a logical sequence for these actions. Use this information to determine if it would be more
efficient to conduct the field investigation in stages.
2.3 OUTPUTS
The outputs of this step are:
• a statement of the decision that will use Superfund environmental data; and
• a list of the actions that will be taken toward remediation or removal of the potential
contamination problem based on the outcome of the field investigation.
15
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CHAPTER 3
STEP 3: IDENTIFY THE INPUTS TO THE DECISION
THE DATA QUALITY OBJECTIVES PROCESS
State the Problem
the ion
tify Inputs to the Decision L
Irt
Optimize the Design for Obtaining Data
3.1 BACKGROUND
The purpose of this step is to:
• identify the informational inputs needed to support the decision; and
• specify which inputs will require new environmental measurements.
The conceptual understanding of the site (i.e., conceptual site model), developed in Step 1:
STATE THE PROBLEM, relates sources and retention or transport media to receptors. This
conceptual understanding of the contamination problem and the decision statement defined in Step 2:
IDENTIFY THE DECISION are previous outputs that are important to consider during this step. The
action level, such as an ARAR or preliminaxy remediation goal(s), is another important input that will
be considered during this step.
I Defin t1i4 tudy Boundaries
Develop a Decisi e I
1
Specify Limits on Decision Errors
IDENTIFY INPUTS
Purpose
Identify the infomiation needed to support the
decision, and specify which Inputs require new
environmental measurements.
Activities
• Identify the In! o mationaI Inputs needed to
resolve the decision.
• Identify sources for each Informational input.
and st those Inputs that are obtained
through environmental measurements.
• Define the basis for establishing
contaminant-specific action levels.
• Identify potential sampling approaches and
appropiiate analytical methods.
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3.2 ACTIVITIES
The following subsections describe suggested activities that will help identify inputs to the
decision.
Identify the Informational Inputs Needed to Resolve the Decision
It is important to determine whether monitoring, modeling, or a combination of these
approaches will be used to support the decision. The decision inputs depend on the approach selected.
For example, data on soil characteristics and hydrogeology could be useful for calibrating a computer
model of contaminant transport and dispersion through ground water. When decisions are supported
by modeling, it may be useful to consider the conceptual site model as a frame of reference. The
conceptual site model summarizes how the site-related contamination may pose a risk to human health
and the environment. Some components of the conceptual site model may be estimated using
mathematical equations and assumptions (i.e., modeling), and other compohent.s will be estimated by
directly measuring some characteristic of the site (i.e., monitoring). The conceptual site model concept
was discussed in Step 1: STATE THE PROBLEM. Based on the selected approach, list all of the
informational inputs needed to support the decision. Diagramming techniques may be used to help
organize the list of inputs into categories and show logical or temporal relationships.
IdentifS’ Sources for Each Informational Input and List Those Inputs That are Obtained
Through Environmental Measurements
Identify existing sources for information that can support the decision. Sources may include
historical records, regulations, directives, engineering standards, scientific literature, previous site field
investigations, or professional judgement.
Determine the Basis for Establishing Contaminant-Specific Action Level(s)
Determine if ARARs are available for the potential contaminants or if preliminary remediation
goals have been developed for the site. If no regulatory threshold or standard can be identified during
this step, the decision maker will need to decide how to develop a realistic concentration goal to serve
as an action level for the field investigation design and evaluation. These action levels will be used as
targets for developing and evaluating the study designs in the last step of the DQO Process.
Identify Potential Sampling Techniques and Appropriate Analytical Methods
Review the decision and associated regulatory objectives identified in Step 2: IDENTIFY THE
DECISION. Use the list of contaminants identified earlier in this step and contaminant-specific action
levels as a preliminary basis for identifying the most appropriate analytical methods. The decision on
analytical methodology will be made in Step 7: OP11MLZE THE DESIGN when more information
about sampling and measurement error is available. Finally, identify potential sampling techniques
and associated equipment.
Further discussion of these decision-specific activities is included in Appendix I, Section C.
18
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3.3 OUTPUTS
The outputs that will result from the activities above include a list of informational inputs
needed to make the decision and a list of environmental variables or characteristics that will be
measured. There is a potential for confusion at this point because the outputs of this step are actually
the inputs to the decision.
Example List of Advanced Assessment Decision, Phase I, Inputs
(1) List of Inputs Needed to Support the Decision:
potential contaminants
-- concentrations in space and time
-- slope factors or dose/response relationships
• exposure pathways
-- media (e.g.. soil, surface water, ground water, air, biota, sediments)
-- rates of migration (within and between media)
-- rates of dispersion/accumulation
• receptors
-- typeslsubpopulations
-- ecosystems
-. sensitivities
-- numbers/densities
-- activity levels/paticms
• preliminary remediation goal/ARARs
• site’s physical and chemical charactenstics that influence technology applicability (e.g.,
presence of organic comçxneni.s. soil permeability, and depth to impervious formation)
(2) List of Inputs That Require New Environmental Measurements:
• contaminant concentrations in space and time for each media of concern
• small- and large-scale vanability in potential contaminant concentrations
• other measurements related to risk assessment, such as fate and transport model
parameters.
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CHAPTER 4
STEP 4: DEFINE THE BOUNDARIES OF THE STUDY
ThE DATA OUAUTY OBJECTIVES PROCESS
E I I L
Define the
Study Boundaries_L
4
It
Optimize the Design tor Obtaining Data
4.1 BACKGROUNI)
The purpose of this step is to define the spatial and temporal boundaries of the study, so as to
clarify the domain of what the samples are intended to represent. In addition, Step 4: DEFINE THE
BOIJNDARLES provides guidance on how to partition a site so as to prevent inappropriately pooling
and averaging data in a way that could mask potentially useful information.
In order for samples to be representative of the domain or area for which the decision will be
made, the boundaries of the study must be precisely defined. The purpose of this step is to clearly
define the set of circumstances (boundaries) that will be covered by the decision. These include:
• Spatial boundaries that define what should be studied and where the samples should be
taken; and
• Temporal boundaries that describe when samples should be taken and what time frame the
study data should represent.
State the Problem
4
Identify the Decision
the Decision
Develo ’Q ç ion Rule
DEFINE BOUNDARIES
Purpose
Specify the spatial and temporal aspects of
the environmental media that the data must
represent to suppo t the decision.
ActMties
• Deftne the geographic areas ol the field
Investigation.
• Specify the characlenstics that define the
population of Interest.
• Divide the population Into strata having
relatively homogeneous characteristics.
Define the scale of decision making.
• Determine the lime liame to wt ith the
decision appfles.
• Determine when to collect samples.
• Identify practical constraints that may
hinder sample estiedlon (reconsider
previous stops as necessary).
Specify Limits on Decision Er j
21
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These boundaries will be used to ensure that the study design incorporates the time periods in
which the study should be implemented, areas that should be sampled, and the time period to which
the study results shouLd apply. This will help ensure that the study data are representative of the
objects or people being studied.
Practical constraints that could interfere with sampling are also identified in this step. A
practical constraint is any hinderance or obstacle that may interfere with the full implementation of the
study design.
Applicable information from previous DQO steps that will be necessary to develop boundaries
includes:
• site contaminant(s) identification;
• potential migration pathways and exposure routes and potential receptors;
• the site’s physical and chemical characteristics that enhance or decrease the likelihood of
contaminant distribution movement within and among media;
• future use of the site;
• the decision(s) identified in the Step 2: IDENTIFY ThE DECISION; and
• the “sampling and analysis action level” or “final remediation/removal action level.”
4.2 ACTIVITIES
Define the Spatial Boundary of the Decision.
Figure 4-1 is a representation of this step
(1) Define the domain or geographic area within which all decisions must apply. The domain
or geographic area is a region dl%tinctlvely marked by some physical features (i.e., volume,
length, width, boundary) to ‘hich the decision will app!y. Some examples are property
boundaries, operable units. aM c posure areas.
(2) Specify the characteristics that define the population of interest. The “population” is a
term that refers to the total colkction of objects or people to be studied, and from which
the sample is to be drawn For instance, a population may be PCB concentrations in soil
at a Superfund site, or blood lead kvels in the exposed human population. Clearly define
the attributes that make up the population by stating them in a way that makes the focus of
the study unambiguous. For example, “the top 12 inches of soil” is less ambiguous than
merely “surface soil”.
Some of the considerations in defining the media of concern are:
• What medium was originally contaminated?
• What inter-media transfer of cross-contamination is likely to have occurred (i.e.,
leaching, transport, etc.)?
22
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1. Define Geographic Area
of the Investigation
2. Define Population
of Interest
3. Stratify the Site
4. Define Scale of
Decision Making
-
Subsurface Soil
FIgure 4-1. Defining Spatial Boundaries.
Property Boundaries
Surface Soil
Area of Low-intensity
Activity
Area of High-intensIty
Activity
23
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(3) When appropriale, divide the population info strata that have relatively homogeneous
characteristics. Using existing information, stratify’ each medium or set of objects into
subsets of categories that exhibit relatively homogeneous properties, such as contaminant
concentrations. Stratification is desirable for studying sub-populations or reducing the
complexity of the problem by breaking it into more manageable pieces. The decision
maker can choose to make separate decisions about each stratum or the entire population.
(4) Define the scale of decision making. The scale of decision making is the smallest area,
volume, or time frame of the media in which the scoping team wishes to control decision
errors. The goal of this activity is to define subsets of media that the scoping team will
make decisions about in order to evaluate health and environmental risks and the cleanup
goals of the site, and, at the same time, meet the constraints of the DQOs. The size may
range from the entire geographic boundaries of the site to the smallest size area that
presents an exposure to the receptor. The size of the scale of decision making is generally
based on:
(A) Risk: Here, the scale of decision making is determined by the relative risk that
exposure presents to the receptor (i.e., the size of the scale is correlated with the
risks that it poses to the receptor). The scale of decision making that is based on
risk is referred to as an “Exposure Unit” (EU). An example of an EU could be a
½-acre potential homestead on a remediated site.
(B) Technological considerations: Here, the scale of decision making is based on the
most efficient area or volume of medium that can be removed or remediated with
the selected technology. These areas or volumes are called Remediation Units
(RUs). An example of an RU is the area of topsoil that can be removed by one
pass of a bulldozer.
(C) Other considerations: Here, the scale of decision making is based on practical
factors or a combination of risk and technological factors that dictate a specific
size. These factors may include “hot spots” whose size should be based on
historical site use.
As an example, consider a study of contaminated soil where the goal is to protect future
residents from exposure and where the future land use is residential. The planning team may set the
scale of decision making to a 14’ by 14’ area (EU) if the children derive most of their exposure from
an outdoor play area of this size. Consequently, the decision that will be made at the site would be
protective of children, a sensitive population in exposure assessment.
Define the Temporal Boundaries of the Decision.
(1) Determine the time frame to which the study data apply. It may not be possible to collect
data over the full time period to which the decision will apply. Therefore the scoping
team must determine the most appropriate time frame that the data should reflect (e.g., the
study data will reflect the condition of contaminant leaching into ground water over a
period of a hundred years).
1 Sira ficaflon is used to reduce tha varithility of contaminant concentrations and therefore reduce the number of samples needed to meet
the hnuts of decision error that wifl be defined in Chapter 1 Decisions art generally m e about an asea the size of the stratum or smaller
24
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(2) Determine when to collect samples. Conditions may vary over the course of a study due
to weather or other factors. Moreover, the study decision may be influenced by the
seasons. For example, a study to measure exposure to volatile organic compounds from a
contaminated site may give misleading information if the sampling is conducted in the
colder winter months rather than the warmer summer months. Therefore the scoping team
must determine the most appropriate time period to collect data that will reflect the
conditions that are of interest.
Identify any Practical Constraints on Data Collection.
These constraints include seasonal or meteorological conditions when sampling is not possible
and the unavailability of personnel, time, or equipment. For example, it could occur that surface soil
samples could not be taken beyond the e4st boundaries of a site under investigation because access to
that area had not been granted by the owner of the adjacent property.
Further discussion of the scale of decision making, including examples, is included in
Appendix I, Section D.
4.3 OUTPUTS
The outputs of this step are:
• a detailed description and physical representation (map) of the geographic limits
(boundaries) of each environmental medium (soil, water, air, etc.) within which the
decision(s) will be made;
• a detailed description of the characteristics that define the population of interest;
• definition of the time period in which samples will be taken and to which decisions will
apply;
• the most appropriate scale of decision making for each medium of concern; and
• description of practical constraints that may impede sampling.
25
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CHAPTER 5
STEP 5: DEVELOP A DECISION RULE
THE DATA QUALITY OBJECTIVES PROCESS
V
[ Optimize the Design for Obtair ing Data
5.1 BACKGROUND
The purpose of this step is to integrate the output from the previous steps of the DQO Process
into a statement that defines the conditions that would cause the decision maker to choose among
alternative actions. The outputs from earlier steps include the actions and the decision from Step 2:
IDENTiFY THE DECISION, the action level from Step 3: IDENTIFY THE INPUTS TO THE
DECISION, and the scale of decision making from Step 4: DEFINE THE STUDY BOUNDARIES.
5.2 ACTIVITIES
Specify the Statistical Parameter that Characterizes the Population of Interest
The statistical parameter of interest is a descriptive measure (such as a mean, median,
proportion, or maximum) that specifies the characteristic or attribute that the decision maker would
like to know about the statistical population. Review the study objectives to determine if a particular
statistical parameter is implied or stated. Consult other members of the planning team, such as a risk
State the Problem
3
Identify the
Decision
Identify Inputs to the D st6 ’]
I DefinejDe dy Boundaries
Develop a Decision Rule
Specify Limits
73
DEVELOP A DECISION RULE
Purpose
Develop a logical if...then . statement
that del nes the conditions that would cause
the dedslon maker to choose among
alternative actions.
Actlvflies
• Specify the parameter otinterest
(such as mean, median, maximum,
or proportion).
• Specify the action level for the decision.
• Combine the outputs 01 the previous 000
steps Into an 1f...then... decision rule
that Includes the parameter of Interest.
the action level, and the alternative actions.
27
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assessor or person with statistical training, to determine the most appropriate statistical parameter for
the problem.
Appendix I. Section E, contains additional information on choosing a population parameter.
Specify the Action Level (Final Remediatlon Level or Removal Action Level) for the Decision
The action level is the contaminant concentration which, if exceeded, would indicate that
action should be taken at the site (the action prescribed in Step 2: ll)ENTIFY ThE DECISION).’
If the decision maker believes that the fmal remediation level could be one of two different
levels, then the more stringent one should be chosen for the action level. A more stringent action
level will require analytical methods (detection limits) that would satisfy the less stringent action level
as well. If multiple contaminants are of concern and ARARs are not available or not sufficiently
protective, risk-based PROs need to be developed. Refer to the Risk Assessment Guidance for
Superfund Volume 1-Human Health Evaluation Manual, Part B, Development of Preliminary
Remediation Goals.
Combine the Outputs from the Previous DQO Steps and Develop a Decision Rule
Recall the actions specified in Step 2: fl)ENTIFY THE DECISION. Combine the actions,
sampling and analysis action level, and the parameter of interest (including the scale of decision
making) in a statement that describes the conditions that would lead to a specific course of action. An
example of a decision rule for a Superfund site is, “If the mean PCE concentration of each
downgradient well is greater than the upgradient well, then further assessment and response is
required; otherwise recommend SEA.”
5.3 OUTPUTS
The output for this step is an “if. ..then...” statement that defines the conditions that would
cause the decision maker to choose among alternative courses of action. It should include the
decision, the actions, the parameter of interest, the action level, and the scale of decision making. For
example, if the mean concentration of contaminants in sediments within the stream reach the
ecological screening level(s), then recommend that the site warrants consideration of further assessment
on a response action.
‘This action level is not the final remedialion leveL The final remediation level is not determined until the ROD Rather. this action
level is an assumption made dwing planning based on the decision maker’s capccwion or the final rcmcdiauon level. The action level is
only an assumption, and does not bind the decision maker to a specific value (or the final remediation level
28
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CHAPTER 6
STEP 6: SPECIFY LIMITS ON DECISION ERRORS
THE DATA QUAUTY OBJECTIVES PROCESS
Identity the Decision
/
Identify Inputs to thy 6 ecision
Define the $f dy Boundaries
/
a Decision Rule
cify Limits on Decision ErroraJ
/
/
I f — ---- -- -- ---
SPECIFY LIMITS
ON DECISION ERRORS
Purpose
Specify the decisIon makers acceptable Ilmtts
on decision errors, which are used to
establish appropnate performance goals for
limiting uncertainty in the data.
ActMtles
• Determine the possible range of the
parameter of Interest
• Define both types of decision errors and
Identify the potential consequences of each.
• Specify a range of possible parameler values
where the consequences of decision errors
are relatively minor (gray region).
• Assign probability values to points above and
below the action level that reflect
the acceptable probability for the
occurrence of dedsion errors.
• Check the limits on decision errors to ensure
that they accurately reflect the decision
makeifs concern about the relative
consequences for each type of decision error.
Optimize the Design for Obtaining Data
6.1 BACKGROUND
The purpose of this step is to specify the site manager’s acceptable decision error rates based
on a consideration of the consequences of making an incorrect decision. These limits will be used in
Step 7: OP11MIZE THE DESIGN to generate the most resource-effective sampling design.
Site managers are interested in knowing the true state of some feature of a site. Since
measurement data can only estimate this state, however, decisions that are based on measurement data
could be in error (decision error). Therefore, the goal of the scoping team is to design a sampling plan
that limits the chance of making a decision error to an acceptable level. This step of the DQO Process
will help the site manager define what constitutes acceptable limits on the probability of making a
decision error.
There are two reasons why the site manager cannot know the true value of a population
parameter:
(1) The population of interest almost always varies overtime and space. Limited sampling will
miss some features of this natural variation because it is usually impossible or impractical to
measure every point of a population or to measure over all time frames. Sampling error
State the Problem
A
29
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occurs when sampling is unable to capture the complete scope of natural variability that exists
in the true state of the environment.
(2) A combination of random arid systematic errors inevitably arises during the various steps of
the measurement process, such as sample collection, sample handling, sample preparation,
sample analysis, data reduction, and data handling. These errors are called measurement errors
because they are introduced during measurement process activities.
The combination of sampling error and measurement error is called total study error , which is directly
related to decision error.
The probability of making decision errors can be controlled by adopting a scientific approach.
The scientific method employs a system of decision making that controls decision errors through the
use of hypothesis testing. In hypothesis testing, the data are used to select between one condition of
the environment (the baseline condition or null hypothesis, HJ and the alternative condition (the
alternative hypothesis, H.J. For example, the site manager may decide that a site is contaminated (the
baseline condition) in the absence of strong evidence (study data) that indicates that the site is clean
(alternative hypothesis). Hypothesis testing places the greater weight of evidence on disproving the
null hypothesis or baseline condition. Therefore, the site manager can guard against making the
decision error that has the greatest undesirable consequence by setting the null hypothesis equal to the
condition that, if true, has the greatest consequence of decision error.
A decision error occurs when the measurement data lead the site manager to reject the null
hypothesis when it is true, or to fail to reject the null hypothesis when it is false. These two types of
decision errors are classified as false positive errors and false negative errors, respectively.
False Positive Error — A false positive error occurs when sampling data mislead the site
manager into believing that the burden of proof ii been satisfied and that the null hypothesis (H 0 or
baseline condition) should be rejected. Consider an example where the site manager presumes that
concentrations of contaminants of concern exceed the action level (i.e., the baseline condition or null
hypothesis is: concentrations of contaminants of concern exceed the acuon level). If the sampling
data lead the site manager to incorrectly conclude that the concentrations of contaminants of concern
do not exceed the action level when they actually do exceed the action level, then the site manager
would be making a false positive error. A statistician usually refers to the false positive error as alpha
(a), the level of significance, the size of the critical region, or a Type I error.
False Negative Error — A false negative error occurs when the data mislead the site manager
into wrongly concluding that the burden of proof has been satisfied so that the null hypothesis (I-U
is not rejected when it should be. A false negative error in the previous example occurs when the data
lead the site manager to wrongly conclude that the site is contaminated when it truly is not. A
statistician usually refers to a false negative error as beta (a), or a Type fl error. It is also known as
the complement of the power of a test.
White the possibility of making decision errors can never be totally eliminated, it can be
reduced. To reduce decision errors, the scoping team must develop an acceptable estimate of the
population parameter. This can be accomplished by collecting a large number of samples (to reduce
sampling error) and by analyzing individual samples several times using more precise laboratory
methods (to reduce measurement error). Better sampling designs can also be developed to collect data
that more accurately and efficiently represent the population of interest, Reducing decision errors,
however, generally increases costs. En some cases, reducing decision errors is unnecessary for making
30
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a reasonable decision. For instance, if the consequences of decision errors are minor, a reasonable
decision could be made based on relatively crude data. Similarly, if the consequences of decision
errors are severe 1 the site manager will want to develop a sampling design that eliminates as much
sampling and measurement error as possible (within budget constraints).
A site manager must balance the desire to limit decision errors to acceptable levels with the
cost of reducing decision errors. To find the best balance and thereby efficiently determine whether to
reduce sampling and/or measurement error, the site manager must define acceptable probabilities of
decision errors. Once the acceptable probabilities of decision errors are defined, then the effort
necessary to reduce sampling and measurement errors to meet these limits can be quantified in Step 7:
OPTIMIZE THE DESIGN. It may be necessary to iterate between Step 6 and Step 7 more than once
before an acceptable balance between limits on decision errors and the cost of a sampling design can
be achieved.
6.2 ACTIVITIES
The combined information from the activities section of this chapter can be graphically
displayed onto a “Design Performance Goal Diagram” (Figures 6-1 and 6-2), or charted in a “Decision
Error Limits Table” (Tables 6-1 and 6-2). The activities section will refer to these figures and cables
to help the reader understand the relationships between the activities and the outputs of this step.
Determine the possible range of the parameter of interest.
Establish the possible range of the parameter of interest by estimating its upper and lower
bounds. This means defining the lowest (typically zero in environmental studies) and highest
concentrations at which the contaminant(s) is expected to exist at the site. This will help focus the
remaining activities of this step on only the relevant values of the parameter. Use historical data,
including analytical data, if available. For example, the range of the parameter shown in Figures 6-1
and 6-2 and Tables 6-1 and 6-2 is between 0 and 210 ppm. Note that when interpreting the Design
Performance Goal Diagram, the concentration values on the horizontal axis represent the true
concentration of the parameter of interest.
Define both types of decision errors and identify the potential consequences of each.
Using the action level specified in Step 5: DEVELOP A DECISION RULE, designate the
areas above and below the action level as the range where the two types of decision errors could
occur. The process of defining the decision errors has four steps:
(I) Define both types of decision errors and establish which decision error has more severe
consequences near the action leveL For instance, the threat of health effects from a
contaminated hazardous waste site may be considered more serious than spending extra
resources to remediate the site. Therefore, a site manager may judge that the consequences of
incorrectly concluding that the concentrations of site-related contaminants do not exceed the
action level are more severe than the consequences of incorrectly concluding that the
concentrations of site-related contamInants exceed the action level.
31
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(2) Establish the true state of nature for each decision error. In the example above, from the site
manager’s perspective, the true state of the site for the more severe decision error will be that
the concentrations of site-related contaminants exceed the action level. The true state of nature
for the less severe decision error is that the Concentrations of site-related contaminants do not
exceed the action level.
(3) Define the true state of nature for the more severe decision error as the baseline condition or
null hypothesis (H 0 the site is contaminated), and define the true state of nature for the less
severe decision error as the alternative hypothesis (H ,= the site is not contaminated). Since
the burden of proof rests on the alternative hypothesis, the data must demonstrate enough
information to authoritatively reject the null hypothesis and conclude the alternative.
Therefore by setting the null hypothesis equal to the true state of nature that exists when the
more severe decision error occurs, the site manager is guarding against making the more
severe decision error.
(4) Assign the terms ‘false positive” arid ‘false negative” to the proper decision errors. A false
positive decision error corresponds to the more severe decision error and a false negative
decision error corresponds to the less severe decision error. The definition of false positive
and false negative errors depends on the viewpoint of the decision maker and the actions that
are taken. Consider the viewpoint where a person has been presumed to be “innocent until
proven guilty” (i.e., H 0 is. innocent. H, is: guilty). A false positive error would be convicting
an innocent person; a false negative error would be not convicting the guilty person. From a
decision maker’s viewpoint the errors are reversed when a person is presumed to be “guilty
until proven innocent” (i.e. H, is guilty, H, is: innocent). Here, the false positive error
would be not convicting the guilty person and the false negative error would be convicting the
innocent person.
Define and evaluate the potential cun .equences of decision errors at several points within the
false positive and false negative ranges For e’.ample, the consequences of a false positive decision
error when the true parameter value is rnrrels 10% above the action level may be minimal because it
would cause only a moderate increase in the nsk to human health. On the other hand, the
consequences of a false positive error when the true parameter is ten times the action level may be
severe because it could greatly increase the exposure risk to humans as well as cause severe damage to
a local ecosystem. In this case, site rnan gers would want to have less control (tolerate higher
probabilities) of decision errors of relatively small magnitudes and would want to have more control
(tolerate small probabilities) of decision errors of relatively large magnitudes.
The action level has been set at 100 ppm in Figures 6-1 and 6-2. (Note that the action level is
represented by a vertical dashed line at 100 ppm.) Figure 6-1 shows the case where a site manager
considers the more severe decision errors to occur above the action level. Figure 6-2 shows the case
where the site manager considers the more severe decision error to occur below the action level. The
hypothesis test for the second case is the reverse of the first case, so the false positive and false
negative errors are on opposite sides of the action level. This chapter will focus on Figure 6-1 for
illustrative purposes.
32
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Specify a range of possible parameter values where the consequences of decision errors are
relatively minor (gray region).
The gray region is a range of points (bounded on one side by the action level) where the
consequences of a false negative decision error are relatively minor. Establish the general location of
the gray region by evaluating the consequences of wrongly concluding that the baseline condition (the
null hypothesis) is true.
The gray region establishes the minimum distance from the action level to which the site
manager would like to control decision errors. In statistics, this distance is called delta (6), and is an
essential part of the calculations needed to determine the number of samples that need to be collected.
The width of the gray region reflects the site manager’s concern for decision errors. A more narrow
gray region implies a desire to conclusively detect the condition when the true parameter value is close
to the action level. When the sample estimate of the parameter falls within the gray region, the site
manager may have a high probability of making a decision error (i.e., the data may be “too close to
call”), and may wrongly conclude that the baseline condition is true.
The gray region is an area where it will not be feasible or reasonable to control the false
negative decision error rate to low levels because the resources that would be required would exceed
the expected costs of the consequences of making that decision error. In order to determine with
confidence whether the true value of the parameter is above or below the action level (depending on
the more severe decision error), the site manager would need to collect a large amount of data,
increase the precision of the measurements, or both. If taken to an extreme, the cost of collecting data
can exceed the cost of making a decision error, especially where the consequences of the decision
error may be relatively minor. Therefore, the site manager should establish the gray region by
balancing the resources needed to “make a close call” versus the consequences of making that decision
error.
In Figure 6 -1, the gray region has been set below the action level in the area where the site
manager has determined that the decision errors have the least consequence. The width of the gray
region indicates that the site manager does not wish to control decision errors when the true
concentration at the site is between 80 and 100 ppm.
Assign probability values to points above and below the action level that reflect the acceptable
probability for the occurrence of decision errors.
Assign probability values to points above and below the action level that reflect the site
manager’s acceptable limits for making an incorrect decision. The most stringent limits on decision
errors that are typically encountered for environmental data are .01 (1%) for both the false positive and
false negative decision errors (a and 3). This guidance recommends using .01 as the starting point for
setting decision error rates.’ The most frequent reasons for setting limits greater than .01 are that the
consequences of the decision errors may not be severe enough to warrant setting decision error rates
that are this stringent. If the decision is made to relax the decision error rates from 01 for false
positive and false negative decision errors, the scoping team should document the rationale for setting
the decision error rate. This rationale may include potential impacts on cost, human health, and
ecological conditions.
‘The value of 01 should ! be considered a prescnptive value for setting decision error rates, nor should it be
considered as the policy of EPA to encourage the use of any particular decision error rate.
33
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Repeat this activity for both sides of the gray region. Generally, the acceptable limits for
making a decision error should decrease as the consequences of a decision error become more severe
further away from the action level.
Figure 6-1 shows that from the action level to a true value of 150 ppm for the parameter of
interest, the site manager will tolerate a 5% chance of deciding that the true value is below the action
level, based on field investigation data. If the true value is greater than 150 ppm, the site manager
will tolerate only a 1% chance of deciding the true value is really below the action level. Below the
action level, from 60-80 ppm the site manager will tolerate deciding the true value is above the action
level 10% of the time, and between 40-60 ppm the site manager will allow a false negative decision
error rate of 5%.
Check the limits on decision errors to ensure that they accurately reflect the site manager’s
concerns about the relative consequences for each type of decision error.
The acceptable limits on decision errors should be smallest (i.e., have the lowest probability of
error) for cases where the site manager has greatest concern for decision errors. This means that if
one type of error is more serious than another, then its acceptable limits should be smaller (more
restrictive). In addition, the limits on decision errors are usually largest (high probability of error can
be tolerated) near the action level, since the consequences of decision errors are generally less severe
as the action level is approached. Verify that the site manager’s acceptable limits on decision errors
are consistent with these principles.
The Design Performance Goal Diagram (which is sometimes called a “Decision Performance
Curve”) can be refined by breaking the “steps” of decision errors into smaller units. This would have
the effect of adding rows of information to its corresponding Decision Error Limits Table. The
information from the diagram will be used in the final step of the DQO Process (Step 7: OPTIMIZE
THE DESIGN) in order to construct a statistically based evaluation of how well the sampling design
will meet the DQOs. This evaluation involves the construction of a power curve, which is a graphical
description of a sampling design’s expected performance. If the power curve lies within the
acceptable regions of the Design Performance Goal Diagram, then the corresponding sampling design
satisfies the site manager’s acceptable limits on decision errors.
Appendix I, Section F. contains additional information on specifying limits on decision errors.
6.3 OUTPUTS
The outputs from this step are the site manager’s acceptable decision error rates based on a
consideration of the consequences of making an incorrect decision. These limits on decision errors
can be expressed in a Decision Error Limits Table or in a Design Performance Goal Diagram.
34
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‘.99
Figure 6.1. An Example of a Design Performance Goal Diagram
(Baseline condition: parameter exceeds action level)
Table 6-1. Decision Error Limits Table Corresponding to Figure 6 -1
—
C
0
c Q
0
—
0.
0.1
0.05
110 I 130 I I
100 120 140
Action Level
True Value of the Parameter (Mean Concentration, ppm)
True
concentration
50 to 60 ppm
Correct decision
Acceptable
probability of making
an incorrect decision
( a decision error )
does not exceed
action level
60 to 80
5%
80 to 100
‘I
‘I
10%
100 to 150
gray region—no
probability specified
exceeds action
level
150 to 200
5%
‘I
1%
35
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Figure 6-2. An Example of a Design Performance Coal Diagram
(Baseline condition: parameter less than action level)
Table 6-2. Decision Error Limits Table Corresponding to Figure 6-2
—4)
0
c t iQ
.0
0
I-
. 4)
—
0
0.05
Action Level
True Value of the Parameter (Mean Concentration, ppm)
True
concentration
50 to 60 ppm
Correct decision
Acceptable
probability of making
an Incorrect decision
( a decision error )
does not exceed
action level
60 to 100
5%
100 to 120
II
10%
120 to 150
gray region—no
probability specified
exceeds action
150 to 200
level
20%
‘U
5%
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CHAPTER 7
STEP 7: OPTIMIZE THE DESIGN
THE DATA QUALITY OBJECTIVES PROCESS
4
I .
/
esignforObtaini Dato
7.1 BACKGROUND
The purpose of this step is to identify the most resource-effective sampling design that
generates data which satisfy the DQOs specified in the preceding steps. To develop the optimal
design for this study, it may be necessary to work through this step more than once after revisiting
previous steps of the DQO Process.
This step provides a general description of the activities necessary to generate and select
sampling designs that satisfy the DQOs. In addition, it contains information about how the outputs
from the previous six steps of the DQO Process are used in developing a statistical design. Appendix
I, Section G, discusses the basic principles of developing a statistical design and some basic design
options. This document, however, does not give detailed guidance on the mathematical procedures
involved in developing a statistical sampling design; for this type of guidance, see the references cited
in Appendii I, Section G, or consult with a statistician. Site managers also may want to use EPA’s
DQO Decision Error Feasibility Trials software,’ which provides a first-pass rough estimate of sample
‘U.S. EPA. 1993 Data Quality Objectives Deculon Error Feasthility Trials Software for Personal Computers.
State the Problem 1
1
Identify the Decision
Identify Inputs to the D, ’sion
4/
Define the Stu Boundane ]
Deve p a Decision Rule
/4
I SyhitY Limits on Deciston Erroe 1
OPTIMIZE THE DESIGN
Purpose
Identdy the most resource-effective sa,npflng
and analysis design for generating data that are
expected to satisty the 000s.
ActMt les
• Review the 000 outputs and existing
environmental data.
• Develop general sampling and analysis
design alternatives.
• For each design a emative, venfy that
the DOOs are satisfied.
• Select the most resource-effective design that
satisfies allot the DOOs.
• Document the operational details and
theoretical assumptions at the selected
design in the Sampling and Analysis Plan.
37
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sizes required to satisfy the DQOs. This user-friendly PC software can help speed up the first iteration
through the DQO process.
For most field investigations, a probabilistic sampling approach is necessary for extrapolating
results from a set of samples to the entire site. By combining an efficient probabilistic sampling
design with a statistical hypothesis test, the decision maker will be able to optimize resources such as
funding, personnel, and temporal constraints while still meeting the DQOs. The hypothesis test used
in analyzing the data is an extremely important part of the statistical design, since it provides the
theoretical underpinnings for selecting the number, type, location, and timing of environmental
samples. While it may be true that the hypothesis test may be refined or changed later in the light of
what is discovered when collecting and examining the data, it is essential to have a plan for the
statistical analysis of the data before collecting samples so that the data are more likely to support the
ultimate decision.
For some field investigations, a non-probabilistic (judgmental) sampling approach is
acceptable. A judgmental sampling design consists of directed samples where the decision maker (or
technical expert) selects the specific sampling locations. 2 Typically this occurs when the site manager
wants to confirm the existence of contamination at specific locations, based on visual or historical
information. However, when non-probabilistic sampling approaches are used, quantitative statements
about data quality are limited to the measurement error component of total study error. If the site
manager wishes to draw conclusions about areas of the site beyond the exact locations where samples
were taken, then a probabilistic approach should be used. This will allow the site manager to make
quantitative statement about the sampling error component of total study error, and thus determine the
probability of making a decision error regarding larger areas of the site.
Even if a judgmental sampling design is chosen, it is important to implement all applicable
activities of this step. This will ensure that the qualitative data quality objectives, such as budget,
schedule, and the temporal and spatial constraints (boundaries) are met. In addition, this step will help
the scoping team document:
1. the reasons for selecting a non-probabilistic sampling approach;
2. the reasons for selecting specific sampling locations; and
3. the expected performance of the sampling design with respect to the qualitative DQOs.
7.2 ACTIVITIES
Review the DQO Outputs and Existing Environmental Data
The outputs from the previous steps of the DQO Process provide a succinct collection of
information that is used to develop the sampling design in the following way:
The limits on decision errors provide crucial information for selecting the number of
samples to be collected, the number of analyses per sample, and the hypotheses to be
tested.
2 Gnd samples or transect samples contain an element of randomization because the initial sampling point is chosen
randomly. Thcrcforc they ate considered probabilistic designs, not judgmental.
38
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• The inputs, boundaries, and decision rule are used in deciding the location and timing of
samples.
Therefore, the scoping team should review the previous DQO outputs and confirm the budget for
sampling and analysis, and the project schedule (especially deadlines). List any logistical or
administrative limitations, such as weather, equipment, and personnel availability identified in Step 4:
DEFINE THE BOUNDARIES. Site characteristics, previous sample locations, quality control data,
and audit reports from earlier field investigations also provide valuable information to the sampling
design team (or statistician).
For probabilistic sampling designs, additional information will be needed regarding the
expected variability of contaminants. Consequently, any existing environmental data from the site (or
from similar sites) should be reviewed. Information about existing environmental data may have been
identified during Step I: STATE THE PROBLEM and Step 3: IDENTIFY THE INPUTS. If no
existing data are available, it may be necessary to conduct a limited field investigation to develop an
adequate estimate of variability.
Develop General Sampling and Analysis Design Alternatives
The sampling design team will develop alternative sampling and analysis designs that could
generate data needed to test the hypothesis. To generate alternative designs, the statistician may vary
several different aspects of the design, such as the number and locations of samples collected in the
field, the types of samples collected, or the number of replicate analyses performed on samples.
For each sampling design, a statistical model should then be developed that describes the
relationship of the measured value to the “true” value. This mathematical formulation clarifies how
data generated from a design is to be interpreted and processed in testing the hypothesis. A tentative
analytic form for analyzing the resulting data (for example, a student’s t-test or a tolerance interval)
should also be specified. Use this information to solve for the minimum sample size that satisfies the
decision maker’s limits on decision errors. If the design involves multiple subsample sizes (e.g., for
stratification schemes), then select the optimal mix of subsample sizes.
It is important not to rule out any alternative analytical or field sampling methods due to
preconceptions about whether or not the method is “good enough.” It must be remembered that the
objectives of the statistical design are to limit the total error, which is a combination of sampling and
measurement error, to acceptable levels. Traditional laboratory methods tend to minimize
measurement error, but they can be so expensive that only a limited number of samples can be
analyzed within the budget. There often may be advantages to using less precise methods that are
relatively inexpensive, thereby allowing a significantly larger number of samples to be taken. Such a
design would trade off an increase in measurement error for a decrease in sampling error. Given the
large amount of natural variability in many environmental studies, this approach may reduce overall
costs while limiting the total decision error rates to acceptable levels just as well as a design based on
traditional laboratory methods.
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For Each Design Alternative, Verify that the DQOs are Satisfied
Venfy that each design alternative satisfies all of the DQOs, including limits on decision
errors, budget, schedule, and practical constraints. If none of the designs satisfy the DQOs, the
scoping team may need to:
• increase the acceptable decision errors rates;
• increase the width of the gray region;
• relax other project constraints, such as available personnel;
• increase funding for sampling and analysis; or
• change the boundaries; it may be possible to reduce sampling and analysis costs by
changing or eliminating subgroups that will require separate decisions.
Select the Most Resource-Effective Design that Satisfies All of the DQOs
The design team should perform a sensitivity analysis on the alternative designs to see how
each design performs when the assumptions are changed, together with the impact on costs and
resources. Typically, this means changing certain parameters within some reasonable range, and
seeing how each of these changes influences the expected decision error rates. For example, if the
contaminant variability is higher or lower than assumed for the design, what happens to the design
performance? Or, if the fmal remedial level is more/less stringent than the assumed action level, what
happens to the design performance? A Statistical Power Curve is a useful statistical tool used to
evaluate whether a sampling design has the ability to meet the DQOs. 3 An example of a Power
Curve is shown in Figure 7-1.
Evaluate the design options based on cost and ability to meet the DQO constraints and select
the most resource-effective design among the alternatives. The “most resource-effective” may be the
lowest cost alternative that meets the DQOs, or it may be a relatively low-cost design that still
performs well when the design assumptions change.
Document the Operational Details and Theoretical Assumptions of the Selected Design in the
Sampling and Analysis Plan
Once the final design has been selected, it is important to ensure that the design is properly
documented. This will improve efficiency and effectiveness of later stages of the data collection and
analysis process, such as the development of field sampling procedures, quality control procedures, and
statistical procedures for analysis of the data. The key to successful design documentation is in
drawing the link between the statistical assumptions on which the design is based and the practical
activities that ensure that these assumptions generally hold true.
The operational requirements for implementing the sampling design are documented in the
Field Sampling Plan and the Quality Assurance Project Plan, both of which are included in the
Sampling and Analysis Plan. Design elements that must be documented include:
• sample types (e.g., composite vs. grab samples);
3 A Power Curve provides a graphical depiction of the sensitivity of a design, the steeper the curve, the more sensitive the
design will be in detecting conditions when the baseline (null) hypothesis should be rejected.
40
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I
Figure 7-1 . An Example of a Power Curve
• general collection techniques (e g, split spoon vs. core drill, or activated charcoal media
vs. evacuated canister);
• sample support (i .e., the amount of matenal to be collected for each sample);
• sample locations (surface coordinates and depth) and how the locations were selected;
• timing issues for sample collection, handling, and analysis;
• analytical methods (or performance standards); and
• quality assurance and quality control needs.
For probabilistic sampling designs, the statistical model and assumptions must also be
documented. This item is often omitted, yet it can be one of the most important aspects of the design
documentation. If the theoretical basis for the design is documented, then the project team has a basis
for handling unexpected problems that ü evitably arise in the field. This will help maintain the overall
validity of the study in the face of unavoidable deviations from the original design.
0.7
0.9
0.8
0) c
- 0
0.6
:1 ::
0.2
W a-
0.1
0.05
0.5
Action Level
True Value of the Parameter (Mean Concentration, ppm)
41
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7.3 OUTPUTS
The outputs for this step include the optimal (most resour e-effeccive) sampling design for the
field investigation, along with documentation of the key assumptions underlying the design. The data
collected using this design are expected to be “adequate” for the site manager’s or other decision
maker’s needs.
7.4 SUPERFUND DATA CATEGORIES
During the sampling design step, the design team identified design elements that relate to
QA/QC procedures. As explained later in Chapter 8, these QAIQC-related design elements are
combined with other required QA/QC procedures, arid the complete set of QA/QC requirements for the
project are incorporated into the quality assurance project plan (QAPP). The DQO Process provides a
logical basis for linking QA/QC procedures to the intended use of the data, primarily through the
decision maker’s acceptable limits on decision errors. The translation of the site manager’s acceptable
limits on decision errors into specific QA/QC requirements is done during Step 7: OPTIMiZE THE
DESIGN and completed in the QAPP development process. 4
To assist in the interpretation of data, the Superfund program has developed the following two
descriptive data categories:
• Screening data with definitive confirmation;
• Definitive data.
These two data categories are associated with specific quality assurance and quality control
elements, and may be generated using a wide range of analytical methods. The particular type of data
to be generated depends on the qualitative and quantitative DQOs developed during application of the
DQO Process. The decision on the type of data to be collected should not be made prior to
completion of the entire DQO Process.
Screening Data with Definitive Confirmation
Delmition of Screening Data
Screening data are generated by rapid, less precise methods of analysis with less rigorous
sample preparation. Sample preparation steps may be restricted to simple procedures such as dilution
with a solvent, instead of elaborate extraction/digestion and cleanup. Screening data provide analyte
identification and quantification, although the quantification may be relatively imprecise. At least 10%
of the screening data are confirmed using analytical methods and QA/QC procedures and criteria
associated with definitive data. Screening data without associated confirmation data are not considered
to be data of known quality.
For more information about the QAPP development process, see Guidance for Preparing, Reviewing, and Implementing
Quality Assurance Project Plans for Environmental Programs, EPAIQA/G•5 (Draft).
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Screening Data QAJQC Elements
• Sample documentation (location, date and time collected, batch, etc.);
• Chain of custody (when appropriate);
• Sampling design approach (systemaflc, simple or stratified random, judgmental, etc.);
• Initial and continuing calibration;
• Determination and documentation of detection limits;
• Analyte(s) identification;
• Analyte(s) quantification;
• Analytical error determination: 1 An appropriate number of replicate aiiquots, as specified
in the QAPP, are taken from at least one thoroughly homogenized sample, the replicate
aliquots are analyzed, and standard laboratory QC parameters (such as variance, mean, and
coefficient of variation) are calculated and compared to method-specific performance
requirements specified in the QAPP;
• Definitive confirmation: at least 10% of the screening data must be confirmed with
definitive data as described below. As a minimum, at least three screening samples
reported• above the action level (if any) and three screening samples reported below the
action level (or as non-detects, ND) should be randomly selected from the appropriate
group and confirmed.
Definitive Data
Definition of Definitive Data
Definitive data are generated using rigorous analytical methods, such as approved EPA
reference methods. Data are analyte-specific, with confirmation of analyte identity and concentration.
Methods produce tangible raw data (e.g., chromatograms, spectra, digital values) in the form of paper
printouts or computer-generated electronic files. Data may be generated at the site or at an off-site
location, as long as the QAJQC requirements are satisfied. For the data to be definitive, either
analytical or total measurement error must be determined.
Definitive Data QAJQC Elements
• Sample documentation (location, date and time collected, batch, etc.);
• Chain of custody (when appropriate);
• Sampling design approach (systematic, simple or stratified random, judgmental, etc.);
• Initial and continuing calibration;
• Determination and documentation of detection limits;
• Analyte(s) identification;
• Analyte(s) quantification;
• QC blanks (trip, method, rinsate);
• Matrix spike recoveries;
• Performance Evaluation (PE) samples (when specified);
The procedures idcnti( ed here measure the precision of the analytical method, and are required when total measurement
error is not determined under confirmation step.
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• Analytical error determination (measures precisLon of analytical method): An appropriate
number of replicate aliquot.s, as specified in the QAPP, are taken from at least one
thoroughly homogenized sample, the replicate aliquots are analyzed, and standard
laboratory QC parameters (such as variance, mean, and coefficient of variation) are
calculated and compared to method-specific performance requirements defmed in the
QAPP,
• Total measurement error determination (measures overall precision of measurement system,
from sample acquisition through analysis): An appropriate number of co-located samples
as determined by the QAPP are independently collected from the same location and
analyzed followmg standard operating procedures. Based on these analytical results,
standard laboratory QC parameters such as variance, mean, and coefficient of variation
should be calculated and compared to established measurement error goals. This procedure
may be required for each matrix under investigation, and may be repeated for a given
matrix at more than one location at the Site.
Impact of Data Categories on Existing Superfund Guidance
These Data Categories replace references to analytical levels, quality assurance objectives, and
data use categories. The major documents impacted by the Data Categories are:
- Data Quality Objective Guidance for Remedial Response Activities: Development Process
and Case Studies: EPAJ54O/G-87/003 and 004, OSWER Directive 9355.0-7B;
- Quality AssuranceiQuality Control Guidance for Removal Activities: Sampling QA/QC
Plan and Data Validation Procedures: EPA/540/G-90/004, OSWER Directive 9360.4-01
April 1990; and
- Guidance for Performing Site Inspections Under CERCL4, OSWER Directive 9 .
August 1992.
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CHAPTER 8
BEYOND THE DQO PROCESS:
The Sampling and Analysis Plan and Data Quality Assessment
8.1 OVERVIEW
This chapter explains some important QA management steps that occur after the DQO Process
has been completed. The DQO Process is part of the planning phase of the data collection life cycle,
as illustrated in Figure 8-1. At the completion of the DQO Process, the site manager will have
documented the project objectives and key performance requirements for the data operations in the
DQOs, and will have identified a sampling design that is expected to achieve the DQOs. The
sampling design and DQOs are used to develop the Quality Assurance Project Plan (QA.PP) and the
Field Sampling Plan (FSP), both of which are included in the Sampling and Analysis Plan (SAP). The
SAP provides the detailed site-specific objectives, specifications, and procedures needed to conduct a
successful field investigation. During the implementation phase of the data collection life cycle, the
SAP is executed and the samples are collected and analyzed. During the assessment phase, Data
Quality Assessment (DQA) is performed on the data to determine if the DQOs have been satisfied.
The relationships between the DQO Process and these subsequent activities is explained in more detail
below.
8.2 SAMPLING AND ANALYSIS PLAN DEVELOPMENT
The SAP is a formal Superfund project document that specifies the process for obtaining
environmental data of sufficient quantity and quality to satisfy the project objectives. The DQO
Process can be viewed as a preliminary step in the SAP development process, since it logically
precedes the actual development of the SAP document, as shown in the right half of Figure 8-1. The
outputs of the DQO Process feed directly into the development of the QAPP and the FSP, which are
the two main elements of the SAP. Thus, the SAP is a single document that integrates the DQOs,
QAPP, and FSP into a coherent plan for collecting defensible data that are of known quality adequate
for the data’s intended use.
The Quality Assurance Project Plan
The QAPP is required for all EPA data collection activities. The QAPP contains information
on project management, measurement and data acquisition, assessment and oversight, and data
validation and useabihty. DQOs are a formal element of the QA.PP, yet information contained in the
DQOs relates indirectly to many other elements of the QAPP. In essence, the DQOs provide
statements about the expectations and requirements of the data user (such as a site manager). In the
QAPP, these requirements are translated into measurement performance specifications and QAJQC
procedures for the data suppliers, to provide them with the information they need to satisfy the data
user’s needs.
The Field Sampling Plan
The FSP specifies how to conduct field activities to obtain the environmental data needed for
the project. Whereas the DQO Process generates a sampling design based on the data user’s needs,
the FSP provides the operational plan for executing that sampling design. The FSP identifies
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procedures for collecting samples in a manner that is consistent with the underlying theory and
assumptions upon which the sampling design is based. This, along with the QAJQC procedures
specified in the QAPP, helps ensure that the resulting data will be valid and appropriate for their
intended use.
8.3 DATA QUALITY ASSESSMENT
After the environmental data have been collected and validated in accordance with the SAP,
the data must be evaluated to determine whether the DQOs have been satisfied. EPA has developed
guidance on Data Quality Assessment (DQA) to address this need.’ DQA involves the application of
statistical tools to determine whether the variability and bias in the data are small enough to allow the
site manager to use the data to support the decision with acceptable confidence. The five main steps
of the DQA process are illustrated in Figure 8-2.
U. S. Environmental Protection Agency (EPA). 1993. Guidance for Conducting Environmental Data Quality
Assessments EPA/QA/C-9
Figure 8-1. QA Planning and the Data Life Cycle
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For DQA to be effective and efficient, the crucial groundwork must have been laid in the
planning phase. The DQOs provide the evaluation criteria by which the data will be assessed, and the
SAP provides the blueprint by which the data will be generated. If the planning has been carried out
thoughtfully, and the plans are executed successfully, then the DQA will provide answers that are
useful for the site manager.
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Figure 8.2. The DaLa Quality Assessment
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APPENDIX I
TECHNICAL SUPPLEMENT TO
THE DATA QUALITY OBJECTIVES
PROCESS
SECTION A: STATE THE PROBLEM
THE CONCEPTUAL SITE MODEL AND IRE DQO PROCESS
This discussion focuses on the relationship between the conceptual site model (CSM) and the
DQO process for Phase I of the advanced assessment decision. The DQO process involves a series of
steps that gradually narrows, focuses, and divides a potentially complex problem into manageable
pieces. Site problems can be very complex, especially in cases where contamination is present in
several media or when cross-media contamination exists.
The CSM is developed using readily available (existing) data and illustrates the relationship
between contaminants, retention/transport media, and receptors. The relationship between
contaminants, retention/transport media, potential receptors, and the possibility for exposure to occur is
central to a description of the problem, which is required in the first step of the DQO process.
The CSM also facilitates understanding of why new environmental data may be needed to
resolve the contamination problem. The need for new environmental data may be confirmed by using
the DQO process.
The CSM also serves as a framework for identifying data gaps. Data gaps identified in the
CSM can be addressed by listing them as inputs to the decision in the third step of the DQO process.
Information in the CSM about the location of contamination and potential receptors, as well as
contaminant fate and transport, can be used to establish spatial and temporal boundaries for the field
investigation in the fourth step of the DQO process. In summary, the development of the CSM
directly influences the generation of the outputs of the first four steps of the DQO process.
The following discussion provides more information on developing the CSM and on defining
exposure scenarios.
DEVELOP/REFINE THE CONCEPTUAL SITE MODEL
The following series of tasks are most appropriate for scoping site inspections and Phase I
remedial investigations. In the later phases of the Superfund process, it is most important to confirm
the exposure scenarios and generate a diagram depicting contaminant concentrations superimposed on
a site map.
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(L) Collect existing site data. Gather all historical site data and other pertinent information
and compile an up-to-date data base on the site. Use this information to prepare written
descriptions and graphic illustrations (diagrams) of contaminant sources, migration and
exposure pathways, and potential physical and environmental targets or receptors. These
illustrations and diagrams condense and document the important elements of exposure.
and facilitate identification of the data needed to assess the potential risks of exposure
associated with the site.
(2) Organize, analyze, and interpret existing site data. Organize site data according to:
• information on sources and source types (e.g., landfills, impoundments, lagoons, or
ditches);
• affected media;
• site’s physical and waste characteristics that can influence migration or containment;
and
• potential migration and exposure pathways and receptors.
Surn.rna.rize the analytical results of previous data collection activities with respect to;
• contaminants of interest,
• contaminant concentrations in each media and the practical concentration ranges of
concern;
• anticipated analytical methods, and
• analytical method performance characteristics such as precision, bias, and method
detection limjts.
Perform a site reconnaissance ith photographic equipment to document and gather
current information to detennine wheiher observations are consistent with the current
understanding of the site Dunng the site visit, search for signs of contamination, such as
the appearance of surface s aier. strnscd vegetation, or discolored soil. Use topographic
maps to mark well locations and esiimaie the extent of source areas or the presence of
sensitive environs. Try to uncover tnformatiori that will help assess the apparent stability
of the site, such as leaking containment structures or weakening beams. Conduct limited
sampling with portable equupmeni and gather additional anecdotal information from local
sources that may reveal disposal areas or practices that were previously unknown and
may affect contanunant migration
(3) Determine if existing data can support the conceptual site model. Assess whether a
limited field investigation is needed to adequately define the conceptual site model. This
assessment helps determine whether or not samples need to be collected and, if so, if they
will be used to supplement or verify existing data.
(4) Define the conceptual site modeL The compilation, organization, and interpretation of
historical site data now can be used to develop a diagram that illustrates the conceptual
site model. Representing the linkages among contaminant sources, release mechanisms,
pathways, exposure routes, and receptors in a diagram is a very useful and efficient
technique for summarizing the current understanding of the contamination problem.
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The wntten description should be supported with maps and cross-sections depicting
contaminants and contaminant distribution, as appropriate.
DEFINE EXPOSURE SCENARIOS
(1) Identify media of concern. Use historical site data including analytical data to identify
media that is currently contaminated or that can become contaminated through migration.
(2) Identify the contaminants of concern. Develop a broad list of contaminants known or
suspected to be at the site. A comprehensive approach to identifying contaminants
minimizes missing chemicals that may contribute to overall risk at the site or those that
may not contribute to risk significantly, but are present in large quantities.
(3) Define future land use. Currently, a formula for determining the probable future land
use for a site is unavailable. Therefore, begin by considering the current site land use and
determine if factors such as zoning laws, renovation projects, and anticipated population
growth may influence the future land use for a site. The “Risk Assessment Guidance for
Superfund (RAGS) Human Health Evaluation Manual, Part A” (U.S. EPA, July 1989)
provides more detailed support for defining future land use.
(4) Define Applicable or Relevant and Appropriate Requirements (ARARs). Identify the
ARARs for the site. Start with the current list of contaminants and list all the chemical-
specific ARARs from all the environmental statute.s. Along with the standard, note the
jurisdictional prerequisites under which the ARAR was established. This information will
be used to determine the applicability, relevancy, and appropriateness of the standard for
CERCLA. The search continues beyond chemical-specific ARARs. It should also
include location- and action-specific ARARs. Further assistance in identifying ARARs
for the site is provided in the “CERCLA Compliance with Other Laws Manual” (U.S.
EPA, August 1988).
(5) Assemble exposure scenarios. Identify all available exposure pathways associated with
the site. An exposure pathway describes a unique mechanism by which a receptor is
exposed to site-related contaminants. Each exposure pathway includes:
• a source and release mechanism,
• a retention and transport medium;
• an exposure point; and
• an exposure route.
For each medium and land-use combination, identify the most appropriate exposure
scenarios.
At this point, several components of an exposure scenario have already been identified
and should be brought forward. One of these components is the potential receptor identified in
the conceptual site model. Use the potential receptors and characterize the exposure setting as
it relates to receptor locations and average daily activity patterns. The scoping team also
considers those physical site characteristics and waste characteristics that influence contaminant
migration. Other components of the conceptual Site model that assist this effort are the
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identified sources and affected or potentially contaminated media. Once these exposure-related
elements have been identified, consider receptor locations and activity patterns and any point
of potential contact with these media. After defining all potential exposure points, identify
probable exposure routes (i.e., ingestion, inhalation, dermal contact).
Next, assemble all of the information collected above into complete exposure pathways
and combine exposure pathways as appropriate.
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SECTION B: IDENTIFY THE DECISION
RELATIONSHIPS BETWEEN THE DECISION STATEMENTS
AND PRE-SACM SUPERFUND PROCESS
The purpose of the following information is to help users correlate the first three decisions
presented in the guidance to the pre-SACM Superftind process.
Superfund site assessment encompasses identification, evaluation, and response to uncontrolled
releases of hazardous substances and determination of the level of post-cleanup risks to human health
and the environment. To evaluate a site efficiently and minimize unnecessary expenditure of
resources, site assessment activities arc performed in stages or tiers.
According to thc Office of Solid Waste and Emergency Response Interim Guidance on
“SACM Regional Decision Teams” (Publication 9203.1-0-51, December 1992), site response action
options that are based on information or data generated in the early assessment stage (i.e, site
inspection’) include recommending the initiation of RI activities. Therefore, in general, site inspection
and removal data collection activities and the decisions they support occur in the early assessment
stage timeframe. A statement of the early assessment decision is, “Determine whether the release (or
potential release) poses a threat to human health or the environment.” Recognize that a removal action
can occur at any time during site assessment.
The Advanced Assessment Stage activities follow the early assessment. As stated in the
previous paragraph, a remedial investigation 2 data collection activity and the decision it supports
occurs in the Advanced Assessment Phase I timeframe. A statement of the Advanced Assessment
Phase I decision is, “Determine whether contaminant of concern concentrations exceed ARARs or
contaminant concentrations corresponding to the target risk level for the site.”
The Advanced Assessment Phase II data collection activity is conducted only if a
determination is made that contaminant concentrations exceed ARARs or concentrations corresponding
to the target risk level and, as a result, the site warrants a further response action. The Advanced
Assessment Phase II data collection activity occurs in the remedial investigation/feasibility study
timeframe.
SACM Decisions In the Context of the DQO Process
This guidance specifically discusses four site decisions that often require field investigations.
Three are site assessment decisions and the fourth is the cleanup verification decision after the
remedial response action has been completed. This subsection discusses these SACM decisions in the
‘The intcnm guidance also references Preiiminasy Assessment/Removal Assessment as past of the Early Assessment Stage activities
However, this guidance focuses on activities that involve collection of new environmentai data. Typically, new environmental data are not
collected dunng the preliminary assessment Therefoe, this guidance is most concerned with data collection activities in support of , te
inspections and removal assessment during the early assessment stage
2 A combined focused or expanded SI/Ri data collcction can also be conducted dunng the advanced assessment Phase I
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context of the DQO process, along with notations that relate the SACM decisions to the corresponding
phase of the pre-remedial and remedial programs.
Early Assessment (Pre-Remedial) Stage
The early assessment (i.e., removal preliminary assessment or remedial preliminary assessment)
allows site managers to screen sites and select those that warrant further assessment and possible
response action using either the removal and/or remedial authorities. 3 These preliminary assessments
typically are executed without the collection of waste or environmental samples. Instead, they rely on
the collection of readily available information and therefore are unlikely to realize the full benefit of
DQO application. The assessment may result in a decision to recommend the site evaluation
accomplished (SEA) designation or to recommend further assessment and possible response action for
the site. The further assessment rccomrnendatiori may involve collection of additional data to perform
a focused site inspection (SI) or an expanded site inspection/remedial investigation (ESL’RI), if the site
has a high likelihood of remedial action. The SI and ESURI field investigations usually require the
collection of waste or environmental samples and would benefit from a full application of the DQO
process. A possible response action recommendation may involve an emergency/time-critical removal
action, a non-timecritical early action (removal or early/interim remedial), the initiation of the NPL
listing process concurrent with the early response action or ESI/RI, and/or initiation of enforcement
activities. Generally, it may not be expedient to apply the DQO process to emergencyltime-critical
removal action field investigations. On the other hand, DQOs should be developed for non-time-
critical early action field investigations. 4
Advanced Assessment Stage (Remedial Investigation Phase I)
The field investigations in the advanced assessment stage field investigations are conducted in
phases. The primary purpose of the first phase is to support the risk assessment, which is an input to
the decision on whether the site warrants an additional response action. In this advanced site
assessment stage, the response action recommendation typically involves a non-time-critical removal or
early and/or long-term remedial action. Sites that require a response action enter the second phase of
the advanced assessment.
Advanced Assessment (Remedial Investigation Phase II )
The purpose of the second phase of the advanced assessment is to determine the extent of
contamination that exceeds ARARs or contaminant concentrations corresponding to the target risk
level. Consistent with SACM and streamlining initiatives, this extent of contamination determination
is performed concurrently with the first phase of the advanced assessment.’ The extent of
contamination determination supports alternative development processes of both removal engineenng
evaluation and cost analysis (EEICA) and remedial feasibility studies (FS). 6
iSACM Pubitcanon 9203 1.051. September 1992 “SACM Program Management Update. Assessing Sites Under the SACM,’ page 2.
‘SACM Duccuvc 9203 1-051, September 1992 ‘SACM Program Management Update. Early Action aiid Long-Term Action Under SACM”
‘SACM PubLication 9203 1-051, September 1992 “SACM Program Management Update. Assessing Sites Under the SACM .” page 3.
The extent of contamination decision may also support presumptive remedy and lightnuig ROD streamlining initiatives
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Cleanup Attainment Stage
The final SACM decision that will require new data and be the focus of DQO development is
the cleanup attainment decision. This decision addresses whether final response actions achieved final
remediation levels or removal action levels.
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SECTION C: IDENTIFY THE INPUTS TO THE DECISION
DECiSION-SPECIFIC ACTIVITIES
EARLY ASSESSMENT DECISION
The objective of this field investigation is to evaluate the degree to which the site presents a
threat to human health and the environment.
List the Inputs Needed to Support the Decision
Gather the following information during this phase:
• historical waste generation and disposal practices;
• hazardous substances associated with the site;
• potential sources of hazardous substances;
• important migration pathways and affected media;
• a comprehensive survey of targets;
• critical sample locations for the SI;
• contaminants or waste; and
• PA results.
Identify Informational Sources for Each Decision Input
Compile any readily available information about the site and its surroundings. PA
documentation, records that indicate the contaminants at the site, site photographs, arid anecdotal
evidence are all potential informational sources. For more involved assessments, documentation of
observed releases, observed contamination, and levels of actual contamination at the site will be
required.
Identify the Inputs that will Require New Environmental Measurements
Some of the information identified in the previous activity may require environmental
measurements. List those inputs requiring environmental measurements that cannot be satisfied by
existing data from previous field investigations.
The following lists summarize the outputs for each decision.
List of Early Assessment Inputs
(1) List of Inputs Needed to Support the Decision:
• contaminant or waste migration pathway
• waste
• contaminants
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• action level’
(2) List of Inputs That Require New Environmental Measurements:
• contaminant concentrations
• background concentrations’
ADVANCED ASSESSMENT DECISION: PHASE I
List the Inputs Needed to Support the Decision
This stage of the cleanup process will involve determining the nature and magnitude of
contamination. To do so, it is necessary to identify potential contaminants and determine whether or
not their concentrations exceed ARARs or levels that pose an unacceptable risk. Therefore, the
relevant information includes:
• records indicating the contaminants that might be found at the site;
• information that identifies contaminants actually present at the site;
• information about how contaminant concentrations are distributed among media across the
site;
• ARARs (if they exist) or exposure assumptions that will be used in the preliminary
remediation goal (PRG) calculation;
• toxicity information for each contaminant;
• fate and transport information to be used in assessing exposure; and
• a target risk that provides a preliminary definition of the threshold of unacceptable risk.
Determine whether or not contaminant concentrations exceed ARARs or concentrations
corresponding to the target risk level. If ARARs exist, the decision involves determining if the site
complies with explicit regulatory criteria, such as a Maximum Concentration Limit (MCL) for ground
water near a drinking water well. If ARARs do not exist, and the decision will be based on estimates
of the risks posed by the site, then there may be several alternative methods by which site risks can be
estimated. Each method will require different informational inputs. The following suggested activities
apply to this latter, more complicated case.
• Consider each exposure pathway of concern.
• Identify the variables in the risk calculation for each pathway.
• Decide which variables will be estimated using site-specific information and which
variables will be assigned default values.
• For each variable that will be estimated using site-specific information, determine whether
the estimate will be based primarily on modeling or direct measurement, or both.
‘This applies when a comparison of site contamination levels to background levels is the basis for decision making
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List the sampling and analysis action level. 1 If the decision is based on ARARs, then list the
ARARs; if the decision is based on site-specific risk, then list the target ask level.
List all of the decision inputs needed to determine if the site fails to comply with ARARs or
exceeds the acceptable target risk. In both cases, information on concentrations of contaminants will
be required. If the decision is based on site-specific risk, then information on each input to the PRG
calculation for each exposure pathway will be needed (the work done in developing the decision
support strategy should provide a good stalling point). This will include the contaminant potency
factors, exposure pathways, fate and transport information, receptor types and activity levels or
patterns, and intake parameters.
Identify Informational Sources for Each Decision Input
For ARARs, identify the specific regulation. For risk-based decisions, identify informational
sources for the target risk and each input to the PRG calculation. Sources may include default values
derived from written guidance, historical records, census data, field measurements or observations, or
professional judgement. If the decision support strategy requires site-specific modeling to estimate any
of the variables in the risk calculation, then identify any key model parameters that need to be
esumated using site-specific information.
Determine if existing data from this site or similar sites exist. If the data do exist, evaluate
them qualitatively to see if they appear to be the type that are appropriate for the decision.
List the Inputs That Will Require New Environmental Measurements
Some of the sources identified in the previous activity will include field measurements. List
those inputs that require environmental measurements and that cannot be satisfied by existing data
from previous field investigations.
List of Advanced Assessment Decision, Phase I, Inputs
(1) List of Inputs Needed to Support the Decision:
• potential contaminants
• concentrations in space and perhaps time
• potency factors or doseiresponse relationships
• exposure pathways
• media (e.g., soil, surface water, ground water, air)
• rates of migration (within and between media)
• rates of dispersion/accumulation
This is the conlairunant concentration thai corTe.sportds to the targel nsk level, given various assumptions about exposure and contaitunant
fate, transport, and dispersion mechanisms
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• receptors
• types/subpopulations
• sensitivities
• numbers/densities
• activity levels/patterns
• target risk/ARARs
• site’s physical and chemical characteristics that influence technology applicability (e.g..
presence of organic components, soil permeability, and depth to impervious formation)
(2) List of Inputs That Require New Environmental Measurements:
• contaminant concentrations in space (and perhaps time) for each media of concern
• small- and large-scale vanabtlity in potential contaminant concentrations
• other measurements related to risk assessment, such as fate and transport mo Jel
parameters
ADVANCED ASSESSMENT DECISION: PHASE II (EXTENT OF CONTAMINATION)
Much of the information developed at this stage of the cleanup process builds on the
foundation laid in the previous stage (if DQOs were not developed for Advanced Assessment Phase I,
then it will be necessary to develop some of thax information as part of Phase II ). This decision
addresses the extent of contamination that will require remediation. Consequently, the information at
this stage will be similar in character to Phase I. but will be more specific or refined.
List the Inputs Needed to Support the Decision
To calculate the volume of media that bill require remediation, information will be needed
about the specific locations where contam.nant concentrations exceed ARARs or the sampling and
analysis action levels. Information on rernedal alternative effectiveness, efficiency, and cost also will
be needed.
List the contaminants with concentrations that exceed ARARs or the target risk. If the
decision is based on ARARs, then confirm the list of information required to determine
compliance with the A.RARs for each contaminant. If the decision is based on site-
specific risk, then confirm the list of inputs to the PRG calculation that will be required
to determine the extent of contamination that exceeds the PRO.
• List the engineering information required to determine the effectiveness, efficiency, and
cost of each remedial alternative
• If the removal action level or final remediation level differs from the sampling and
analysis action level, 3 then identify the new inputs required to determine the location and
volume of media that exceed the removal action level or final remediation level.
‘If decision npsn.s were not developed for the Phase I advanced assessment decision, then condu the aenvrnes descnbed above for that phase,
except use the final remedianon level and the selected remedy in place of the prelnunary uoo level and remedial aliernaxjves. respecaively
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• List the inputs needed to determine the volume of media that exceeds ARARs or the
sampling and analysis action level.
• This phase focuses on the extent of contamination that will require remediation. The
approach for determining contaminant concentrations usually will follow directly from the
approach taken in Phase II. For decisions based on site-specific risks, the approach to
estimating risk variables also should be consistent with the approach taken in Phase II.
Identify Sources for Each Decision Input
These sources should be similar to those identified in Phase 1, unless the removal action level
or final remediation level differs greatly from the sampling and analysis action level.
Identify the Inputs that will Require New Environmental Measurements
Examine the inputs derived from environmental measurements and list those inputs that will
not be satisfied by existing data.
List of Advanced Assessment Decision, Phase II, Inputs
(1) List of Inputs Needed to Support the Decision:
• removallremedial technologies or alternatives
• contaminants
• refined exposure assumptions or baseline risk assessment assumptions
• sampling and analysis action level or final remediation level
(2) List of Inputs That Require New Environmental Measurements:
• contaminant concentrations
CLEANUP ATFAINMENT DECISION
This stage addresses a question much different than the previous two stages: Do contaminant
concentrations remaining after the remedial action exceed the final remediation level? Nonetheless, the
information required to answer this question closely parallels the information required in the first two
stages.
List the Inputs Needed to Support the Decision
The removal action level or the final remediation level serves as the criterion for deciding if
the response action is complete; hence the scope of information needed at this stage is less than that
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required in previous stages.’ For the cleanup attainment decision, the primary focus is on the
distribution of contaminant residual concentrations across the site.
List the removal action level or final remediation level for each contaminant and identify
any other decision criteria that may be specified in the Engineering Evaluation/Cost
Analysis (EEICA) or the ROD (for example, the ROD may require that a specific
statistical test be performed to determine if the Site has attained the final remediation
levels).
• List the inputs required to determine if the contaminant concentrations exceed the
removal action level or fmal remediation levels.
• Identify any special concerns, such as the desire to ensure that no hot spots above a
certain size and concentration are left behind.
• List the cleanup attainment decision inputs that require field measurements that will not
be satisfied by existing data.
rdentify Sources for Each Decision Input
Identify the information sources for each of the cleanup attainment decision inputs. It is
unlikely that any existing data will satisfy this need, unless the data were collected during the remedial
action timeframe (such as monitoring data).
List the Inputs that will Require New Environmental Measurements
List the cleanup attainment decision inputs that require field measurements that will not be
satisfied by existing data.
List of Cleanup Attainment Decision Inputs
(1) List of Inputs Needed to Support the Decision:
• removal action levels or final remediation levels for each contaminant
• distribution of contaminant (or surrogate) concentrations
(2) List of Inputs That Require New Environmental Measurements:
• contaminant (or surrogate) concentrations
in previous stages. Information about the risk calculation may have been included, however, this mformaoon is now subsumed within the
removal aclion level or the rinal remediation level Likewise, Advan d Assessment Phase I required information about remedial technologies
and alteriiatives, a1 er the ROD, the remedy has been selected, which reduces the scope of information required to make subsequent decisions.
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SECTION D: DEFiNE THE STUDY BOUNDARIES
Section D provides the scoping team with relevant information about how to develop risk-
based, technology-based, and other scales of decision making. In addition, this section will focus on
defining spatial boundaries and scales of decision making for four media of concern: surface soil,
subsurface soil, surface water, and ground water.
1. SCALES OF DECISION MAKING
The following Section provides relevant information about how to develop risk-based,
technology-based, and other scales of decision making.
RISK-BASED SCALES OF DECISION MAKING
Development of risk-based scales requires substantial input from and relies on the professional
judgement of the risk assessment member of the scoping team. In order to develop risk-based scales
of decision making, the scoping team must evaluate: (1) the daily activity and behavior pattern of the
most sensitive receptor; (2) the exposure pathway and route(s); (3) the current and future media use
designation; and (4) contaminant toxicity values. In some cases, ARARs or a target risk level may be
required to define the scale of decision making.
To make a risk-based decision, the sampling data should be representative of well-defined
areas, volumes, and time periods which the scoping team determines a receptor could be exposed to
given the anticipated use of the site. Since this scale is based on exposure assumptions, they are
referred to as ‘Exposure Units” (EUs). If possible, the EU should represent a direct correlation
between the area of contamination and the exposure that the receptor is likely to receive. Each media
will have its own unique type of EU. As an example, surface soil has an EU that is defined by length,
width, and depth of the surface soil layer.
TECHNOLOGY-BASED SCALES OF DECISION MAKING
If the Advanced Assessment Decision (Phase I) has already been made, the scoping team may
define a scale of decision making based on the technology that was chosen to remediate the site.
Scales of decision making that correspond to these areas are called Remediation Units (RUs). An RU
is defined as the subset of a medium that can reasonably be remediated with the selected remediation
technology (e.g., the minimum volume of soil that can be efficiently removed with a backhoe). RUs
are defined by the scoping team in order to design the most cost-effective remediation design. The
size of the RU will determine the scale of resolution that will be necessary for the sampling plan and
also the amount of material that will ultimately be remediated. For each medium, the optimal size of
an RU can be determined using a relative cost analysis and an estimate of (or assumptions about) the
variability and distribution of contaminants in the media. When the “relative cost” of remediation is
high compared to sample and analysis costs, and the variability of contaminants is fairly high (e.g., a
patchy distribution), studying each RU and remediating only those that are contributing to risk may
substantially reduce costs without decreasing the level of protection of the public. When the level of
variability is very low, the optimal RU size will most likely be the same as the EU.
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OTHER SCALES OF DECISION MAKtNG
In some instances it will be difficult or impossible to directly relate the size or volume of the
media to the exposure of a receptor and there may not be a technological approach that can be
translated into RUs. In these cases, the scoping team must select the scale of decision making that
combines the consideration of risk from exposure with practical considerations about an EU or RU
size. Again, the evaluation of the size or volume of an EU should be based on the future use of the
site (residential, light industriaL recreational, etc.) and the receptors’ activity pattern at the site.
EXAMPLES OF SCALES OF DECISION MAKING
In order to explain the process of setting a scale of decision making, three short examples have
been provided. These examples are only meant to illustrate the concept of the scale of decision
making.
Example #1: Risk-Based Scale of Decision Making
Background — The fictitious site is situated in Montana where a lead smelter has operated
over the past 25 years and contaminated a sire of approximately 35 acres with lead tailings
and ash from the smelter. The smelter site is surrounded by residential homes and it seenis
likely that the site could be used as residential lots in the future. The primary contaminant of
concern on the site is lead in the soil. The exposure pathway is ingestion of soil and the
primary target receptor is small children. One of the primary activities of children that
exposes them to soil is playing in their backyard around areas that are devoid of vegetation.
In this case the risk assessor postulates that the majority of the soil exposure received by a
small child is in an area of the backyard that encompasses the sandbox and swing set.
Given this scenario, it would be reasonable for the scoping team to want to control uncertainty
in the sampling data related to the area or volume where children get the majority of their exposure.
Therefore the scoping team would set the scale of decision making to the 14’-14’ area which is equal
to the average size of a backyard play area. This is a risk based scale of decision making because it is
possible to correlate the scale of decision making with the exposure of the most sensitive receptor.
Example #2: Technology-Based Scale of Decision Making
Lagoon Remediation — A Midwestern Coke Plant discharged process waste water into
lagoons on their property. This resulted in the contamination of sediments with organic
chemicals. Solid wastes from the same process were disposed of in several other lagoons and
landfill areas. These contained organic chemicals as well as inorganic contaminants. The
lagoons and landfill areas are surrounded by a wetland area which is the primary concern as
a receptor for the contamination. There are no human receptors nearby. The site manager
recognizes that the cleanup of the lagoons will involve more than one type of remediasion
practice and is most likely to involve bioremediation and gncineration to reduce the influence
of the organic chemicals.
The scoping team at this site choose to evaluate each lagoon separately based on the
assumption that each lagoon would have homogeneous contamination which could be remediated by a
single, but possibly separate, remediation process. Therefore, each lagoon is considered to be a
distinct RU.
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Example #3: Other Scales of Decision Making
Carolina Transformer — The soil at an aba idoned transformer production and reclamation
facility has been contaminated with PCBs (polychiorinated biphenyls). The expected future
use of the site is light industrial and the major route of exposure is through soil ingestion.
The RPM is most concerned with exposure to children trespassers who play on the site.
In this scenario, the scoping team does not believe that there is a strong correlation between
the size of a soil area and the relative “amount” of exposure that the children will receive. However,
from the anticipated site activities of the children, they can select a size area (scale) that would be
protective under the RME if that area had an average concentration of PCBs below the sampling and
analysis action level. For this site, the scale of 1/2 acre was chosen as the Scale of Decision Making.
While this decision was based on some assumptions or risk and the consideration of the receptor’s
activities, the scoping team had to finally make an estimate of the size area that would be protective of
the children rather than rely on a direct correlation between soil area and risk. This is what
differentiates this example from example #1, the risk-based scale of decision making.
2. MEDIA-SPECIFIC BOUNDARY DEVELOPMENT
This section provides specific information or considerations that are useful for the development
of boundaries for specific media. Each medium is treated as a separate chapter. It is useful to have
defined the geographic area of the investigation before using this section.
Surface soil and subsurface soil ar e treated separately in this guidance. Direct contact
exposure to contaminants in surface soil through Ingestion, inhalation of airborne particulate and
dermal absorption exposure routes is the pnma.r focus of the subsequent discussion. Subsurface soil
discussions, on the other hand, prirnanly fxus on indirect exposure routes through other media such
as ground water.
(a) SURFACE SOIL
The media-specific boundar) development for surface soil will provide relevant information to
help the scoping team define spatial boundanes and the scale of decision making for surface soil.
DEFINING THE MEDIA
The physical attributes that define surface soil include grain size, depth, relationship to water
(i e., sand or sediment), organic material content, etc. The scoping team should consider how to
classify objects that appear in surface soil, such as rocks or debris, and whether or not they should be
sampled and/or remediated. The depth of soil that is classified as “surface soil” may be regulated or
standardized in some states or regions. Be sure to check with the proper offices and obtain the
necessary approval before making this decision.
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DEFINE THE SCALE OF DECISION MAKING FOR SURFACE SOIL
Below are descriptions of how to define the scale of decision making for surface soil.
Risk-Based Scales of Decision Making
(1) Identify the future land-use designation and exposure route and determine if it provides a
basis for defining an exposure area or volume.
(2) Define an area or volume of media within which the receptor is expected to limit his
daily activities or to which the receptor is expected to come into contact during the period
of exposure.
(3) Integrate the information from Steps I and 2 with the professional judgement of the risk
assessor in order to define an exposure area or volume. For example, for residential land
use where soil ingestion is determined to be the primary pathway of exposure, young
children may get the majority of their exposure from a typical yard area. A case where a
typical plot size was recommended as such an exposure area can be found in the Risk
Assessment Guidance for Supeifund: Human Health Evaluation Manual (EPA July 1989)
in Chapter 6, Section 6.5.3, page 6-28. If the site-specific plot size is 1 /3-acre, then the
1 /3-acre should be considered an estimate for the scale of decision making.
(4) Modify any estimated scales of decision making with information collected during the site
visit and information that may have been collected by the Agency for Toxic Substances
and Disease Registry if human monitoring was conducted. These scales may provide
additional clues about the activity patterns of the receptors.
Where it is difficult to establish a scale of decision making based on land use and receptor
behavior patterns, rely on standard default exposure area values that are available for media-specific
pathways in the Risk Assessment Guidance for Supetfund: Human Health Evaluation Manual, Part A.
Contact the Risk Assessment Workgroup in the Toxics Integration Branch of EPA for their current
work on this topic or use a technology-based approach to define the scale of interest.
Technology-Based Scales of Decision Making
There are two types of technology-based scales of decision making. The first relies on
physical features of a site to suggest the scale. These may be features that divide the site into smaller
units, such as roads, buildings, or other physical impediments, or features that suggest the location of
contaminants, such as lagoons, trenches, or waste pits.
The second technological approach for defining the scale of decision making is driven by the
technology used to remove or clean up the contamination. This approach involves the identification of
the most efficient subset of media or minimum volume of contaminated material that can be removed
(i.e., the minimum amount of soil that can be removed with a backhoe) or remediated with the
selected technology during an operation of the equipment or treatment cycle.
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(b) SUBSURFACE SOIL
This section will describe relevant information to aid the scoping team to develop spatial
boundaries and scale of decision making for subsurface soil.
Because subsurface soil has the potential to distribute contaminants along several exposure
pathways, the development of boundaries must be based on exposure pathways that have been defined
in Step 1: STATE THE PROBLEM. This section will evaluate methods of developing boundaries for
subsurface soil by concentrating on two exposure pathways: 1) Direct Exposure — when the
subsurface soil becomes surface soil through routine building and landscaping operations; and 2)
Indirect Exposure when the contaminants from the subsurface soil leach into the ground water and
present an exposure through surface or drinking water.
Subsurface soil boundaries must be defined in three dimensions. They should be defined
based on the possible exposure scenario. For example, if exposure to subsurfaces soil is expected to
occur as a result of routine building or landscaping, the scoping team may define the subsurface
boundary as the average depth and width of a building foundation. In other cases, the regional
Superfund office may have a standard definition for subsurface soil that includes dimensions and other
attributes. This definition should be reviewed by the scoping team to determine if it is appropriate for
its circumstances.
DEFINING THE MEDIA
The physical features that describe subsurface soil are similar to those that define surface soil.
Refer to the section on surface soil. The depth of soil that is classified as “subsurface soil” may be
regulated in some states or regions. Be sure to check with the proper offices and to obtain the
necessary approval before making this decision.
DEFINE SCALE OF DECISION MAKING FOR SUBSURFACE SOIL — EVALUATION OF
SURFACE SOIL CONTAMINATION BY SUBSURFACE SOIL
Risk-Based Scales of Decision Making
Currently the Risk Assessment Group of the Toxics Integration Branch of EPA is developing
risk-based approaches for studying subsurface soil. Contact their office for the latest developments in
this area.
Technology-Based Scales of Decision Making
The scale of decision making for subsurface soil brought to the surface during building or
landscaping operations is equal to the volume of subsurface soil that could potentially reach the
surface. In order to determine a scale of decision making for subsurface soil, the scoping team must
understand what potential building and ‘andscaping operations might occur based on the future use of
the site. This information, along with the size and depth of the foundation, basement 1 or soil removal
will give the scoping team a good estimate of the volume of soil that will be removed. This
subsurface volume becomes the scale of decision making. The scoping team will then evaluate the
potential health risks that this volume of soil presents when it is removed.
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Once the scale has been set, the scoping team will evaluate how each volume presents
exposure as surface soil based on possible exposure scenarios. For example, the scoping team would
evaluate the possible exposure that the contaminated soil presents by evaluating the range of surface
soil contamination (thickness and extent) and possible contact of receptors spread on the surface.
DEFINE THE SCALE OF DECISION MAIUNG FOR SUBSURFACE SOIL — EVALUATION
OF GROUND WATER CONTAMINATED BY SUBSURFACE SOIL
Risk-Based Scales of Decision Making
Currently the Risk Assessment Group of the Toxics Integration Branch of EPA is developing
risk-based approaches for studying subsurface soil. Contact their office for the latest developments in
this area.
Technology-Based Scales of Decision Making
A technology-based scale of decision making would be one that is defined as the smallest unit
of subsurface soil that could efficiently be remediated to limit the contamination of ground water using
current technology.
(c) SURFACE WATER AND ASSOCIATED MEDIA
Developing boundaries for surface water is particularly difficult because a surface water body
may be either static or dynamic. The dynamic systems can have inputs from non-contaminated and
contaminated sources. Under dynamic or static conditions, the concentration of contaminant of the
water body can be reduced due to dilution or increase through contaminant inputs from other media
such as surface soil, sediment, and ground water. Defining the boundaries of surface water will not
only involve defining the bodies that are contaminated, but also defining the media that have the
potential to contaminate surface water in the future.
This section will describe relevant information to aid the scoping team to develop spatial and
temporal boundaries and scales of decision making for surface water bodies.
DEFThJE THE MEDIA
Some of the physical features that describe surface water are depth, breadth, width, and
volume. In the case where a flowing body of water is being evaluated, the scoping team should
determine the extent (run) where they feel contamination is possible. Use historical information and
existing analytical data to divide the surface water into areas that are relatively homogeneous withm
the geographic area of the investigation. Consider making separate decisions about surface water
based on the sources of contamination or concentration of contamination. Surface water such as lakes
and ponds may be stratified based on depth where contaminants may concentrate. Alternatively,
flowing bodies such as rivers and streams may be stratified based on their proximity to contaminant
sources.
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DEFINE THE SCALE OF DECISION MAKING FOR SURFACE WATER
The scale of decision making for surface water is defined as the smallest unit (volume, depth.
etc.) of surface water or associted media for which the scoping team wishes to limit the probability of
a decision error. For surface water, there are many potential sources of contamination from associated
media. Theref?re. this section will help the scoping team define the scale of decision making for the
associated media as well as the surface water.
Risk-Based Scales of DecisIon Making
Currently the Risk Assessment Group of the Toxics Integration Branch of EPA is developing
risk-based approaches for studying surface water. Contact their office for the latest developments on
this topic.
Technology-Based Scales of Decision Making
The technology scale of decision making for surface soil is defined as the smallest unit of
surface water or other contaminated media that could efficiently be remediated to limit contaminant
exposure to the receptor.
Scales of Decision Making for Surface Water By Source of Contamination
Surface Soil Contamination of Surface Water
It may be useful to delineate watershed areas within the site in order to define areas where soil
contamination may impact the surface water quality. Evaluate both the dissolved and suspended
portions of soil (runoff as well as leachate). In order to evaluate contaminant leaching, it is essential
to have a good understanding of the physical and chemical properties of both the soil and the
contaminant(s). In addition, the scoping team should evaluate the normal and the extreme conditions
on the site such as extreme rain events, flooding, spring runoff, etc.
Ground- Water Contamination of Surface Water
Ground-water contamination of surface water is particularly difficult to study because
contaminant concentration and flow volume are difficult to measure or model with accuracy. In
addition, these parameters may vary over time. It may not be possible in this case to develop a scale
of decision making. In this event, the goal of the scoping team will be to locate the sources of
contamination and to estimate the extent of ground-water contamination.
Sediment Contamination of Surface Water
In evaluating sediment contamination of ground water, the goal of the scoping team is to
determine the quantity of sediment that aLready exists in the river or lake that could possibly
contaminate the surface water through leaching, or the mobilization of the sediment into the surface
water.
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(d) GROUND WATER
Ground water is the most difficult media to evaluaie primarily because it exists within a soil
matrix which is difficult to sample and evaluate. In addition, many of the techniques that are used in
the boundary section such as exposure units do not apply well to the ground-water system.
DEFINE THE MEDIA
This guidance defines boundaries of ground water to include the overall spatial features of
ground-water depth and range, and the temporal aspects of flow, including rate, water table height, and
variation.
DEFINE THE SCALE OF DECISION MAKING
Consult the hydrogeologist and ground-water specialist when considering scales of decision
making for ground water.
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SECTION E: DEVELOP A DECISION RULE
CHOOSING A POPULATION PARAMETER
The first activity in developing a decision rule is choosing the parameter to characterize the
population of interest. Choosing the parameter of interest involves several considerations that are
discussed below.
AVOIDING PREMATURE CONCLUSIONS ABOUT THE STATISTICAL DESIGN
It is important to remember in the discussion that follows that the decision rule is not intended
to constrain the statistical design. Therefore, the decision maker need only specify the population
parameter that corresponds to the decision, instead of specifying a summary statistic. For instance,
instead of specifying “a geometric average”, the decision maker should only specify “a mean”. This
will allow the statistician to choose a summary statistic, either to conform to the assumptions of the
statistical model that underlies the design, or in response to an analysis of the actual data if the design
assumptions are not supported by the data.
CLAR1FYTh G WHAT THE DECISION MAKER REALLY WOULD LIKE TO KNOW
When specifying an appropriate population parameter, the best guideline to follow is to ask the
question, “What would the decision maker really like to know?” If it is an ‘average’ condition across
an area or time interval at the site, then this will be important information in developing the sampling
design. If it is a peak value at the site, then the sampling strategy may be quite different. If the
decision maker wants to know where the “hot spots” exist, then yet another sampling design may be
appropriate. Clarifying what the decision maker would like to know if the true conditions at the site
could be known will help focus the discussion on matters most relevant to the decision rule.
UNDERSTANDING THE IMPLICATIONS OF DIFFERENT STATISTICAL PARAMETERS
Data may be summarized in a variety of ways, and each statistical parameter will have certain
implications regarding the site. Consequently, it is important to specify a parameter that logically
corresponds to the decision at hand. The following examples illustrate this point.
Mean
The mean is a measure of central tendency of a distribution. The mean concentration of a
contaminant often is used by risk assessors as a mathematical model of long-term exposure. It usually
requires fewer samples than other parameters to achieve a similar level of confidence, and is useful
when the contaminated medium is relatively uniform with a small variance. The mean may be
sensitive to extreme values; hence a few high concentrations can significantly raise a mean, while a
number of low values (such as “non-detects”) can reduce the mean. This sometimes gives rise to
concerns about “averaging away” a contamination problem at a site. In addition, the mean is not
representative of a site when there are a large proportion of non-detects.
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Median
The median is another measure of central tendency that is used to estimate the 50th percentile
of a distribution. The median is less sensitive to extreme vaiue.s. and may be appropriate to use when
the contaminants are distributed in a manner that violates the usual assumptions of a bell-shaped
(normal) or lognormal curve.
Percentiles
Percentiles describe conditions where x percent of the distribution is less than or equal to the
percentile value. For ex.ample 1 if a 95th percentile of a contaminant distribution is equal to 400 parts
per million, then 95% of the concentration levels are less than or equal to 400 ppm. Percentiles may
be used to ensure that the “tails” of a distribution are factored into a decision so that, for instance,
“almost all” of the contamination falls bdow a certain threshold value.
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SECTION F: SPECIFY LIMITS ON DECISION ERRORS
ESTABLISHING PROBABILITY LIMITS ON DECISION ERRORS
After defining the gray region, the decision maker will need to determine the acceptable
probabilities of each decision error. In some non-Superfund applications, one or more of these
probabilities will be established by regulation. For example, the RCRA rule for determining whether a
waste is hazardous because of lead contamination specifies that an upper 90% confidence limit on the
mean lead concentration be compared to the standard; this is comparable to specifying a 0.10
probability limit for the false positive decision error. In the Superfluid program, however, these types
of explicit standards usually are not pre-set.
If the acceptable probabilities for decision errors are not established by regulation, the decision
maker will need to set them. Setting the probability limits on decision errors will depend on two main
factors: the relative consequences of each decision error, and the cost of attaining the decision error
rates. When setting the decision error rates, the decision maker must keep in mind that the cost of
attaining the decision error rates should not exceed the consequences of the decision error. Usually
this will require professional judgments about the likelihood of different consequences and the
magnitudes of their corresponding costs and benefits. By using judgment to balance the costs and
benefits of reducing the probability of decision errors versus the costs and benefits of their potential
consequences, the decision maker establishes how definitive or conclusive the data must be in
supporting the decision.
By defining the limits on decision errors for both the null hypothesis and alternative
hypothesis, the decision maker is actually setting limits on two different aspects of the problem. One
of the limits will restrict the decision errors that could cause risk of exposure to inhabitants and the
environment. The other limit will restrict the decision error that would cause unnecessary cleanup of
the site when the actual risks are below regulated standards.
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SECTION G: OPTIMIZE THE DESIGN
This appendix discusses some basic concepts involved in creating a sampling design.
Probability sampling designs and statistical models are discussed and examples of these concepts are
included in the DQO applications at Superfund sites contained in Appendix [ I. In addition, a
discussion on confidence intervals and hypothesis tests is also included to demonstrate the difference
in these techniques. However, methods for creating and analyzing sampling designs and building
statistical models are beyond the scope of this guidance. The reader is referred to Cochran (1977),
Gilbert (1987), and U.S. EPA (1989) for more information. It is recommended that those unfamiliar
with statistical sampling techniques consult a statistician or someone familiar with statistical sampling
designs If certain critical statistical design assumptions are violated, the data may become unusable for
the specified purpose.
I. SAMPLING DESIGNS
NON-PROBABILISTIC SAMPLING
Non-probabilistic sampling (judgmental sampling) involves an expert selecting sample
locations based on experience and knov ledge of the site. The results from these samples cannot be
extrapolated to the entire Site, and it is dirncult to measure the accuracy of any estimates using the
data. However, judgmental samp!es can be used subjectively to provide information about specific
areas of the site, which is generally useful during the preliminary assessment and site investigation
stages if there is substantial information on the contamination sources and history. For instance,
judgmental sampling is useful when the sampling objective is to confirm specific locations of
contamination that have already been idcritif cd through visual or historical information. If arty
statistical conclusions are desired, ho e e,, juJ mental sampling is not applicable.
PROBABILISTIC SAMPLING
Probability sampling designs alk’ i. the results from a set of samples to be generalized to the
entire site. All probability sampling dr’.igns ha e an element of randomization which allows
probability statements to be made about the quality of estimates derived from the data. Every
potential sampling point within the sampling unit has a positive probability of being sampled.
Therefore, probability samples are useful for testing hypotheses about whether a site is contaminated,
the level of contamination, and other common problems that occur with Superfund sites.
There are many different probability sampling designs, each with advantages and
disadvantages. A few of the most basic designs include simple random sampling, sequential sampling,
systematic sampling, and stratified sampling Other probability designs, such as multistage probability
sampling and search sampling, are too complicated to be explained in this guidance. It is
recommended that a statistician be consulted to determine the best design and the most appropriate
analysis.
Simple Random Sampling
The simplest probability sample is the simple random sample. With a random sample, every
possible sampling point has an equal probability of being selected and each sample point is selected
independently from all other sample points. Random sample locations are usually generated using a
random number table or through computer generation of pseudo-random numbers. Simple random
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sampling is appropriate when little or no information is available for a site, and the population does
not contain any trends. If some information is available, simple random sampling may not be the
most cost-effective sampling design available.
Sequential Random Sampling
Sequential random sampling is a variation of simple random sampling. As before, every
possible sampling point has an equal probability of being selected, and sample locations are selected
randomly. However, instead of conducting a hypothesis test with all the data, a decision is made after
each sampling round is collected and measured. This decision can have three possible results: reject
the hypothesis, accept the hypothesis, or continue collecting data. Therefore, it may not be necessary
to collect and analyze all the samples required for a simple random sample.
Sequential sampling designs are useful when analyses are very expensive and not much
information is known about sampling and/or measurement variability. However, this method can only
be used when the contaminant distribution is stable over the sampling time frame.
Systematic Sampling
Systematic sampling achieves a more uniform spread of sampling points than simple random
sampling by selecting sample locations using a spatial grid, such as a square, rectangle, or triangle, in
two or three dimensions. To determine sample locations, a random starting point is chosen, the grid
is laid out using this starting point as a guide, then all points on the grid (grid nodes) are sampled.
Since sampling locations are located at equally spaced points, they may be easier to locate in
the field than simple random samples or other probability samples. However, a systematic sampling
design should not be used if the contamination exhibits any cyclical patterns.
Stratification
Stratified random sampling is used to improve the precision of a sampling design. To create a
stratified sample, divide (he study area into two or more non-overlapping subsets (strata) that cover the
entire Site. Strata should be defined so that physical samples within a stratum are more similar to each
other than to samples from other strata. Sampling depth, concentration level, previous cleanup
attempts, and confounding contaminants can be used as the basis for creating strata. Once the strata
have been defined, each stratum is then sampled separately using one of the above methods.
A stratified sample can control the variability due to media, terrain characteristics, etc., if the
strata are homogenous. Therefore, a stratified random sample may provide more precise estimates of
contaminant levels than those obtained from a simple random sample. Even with imperfect
information, a stratified sample can be more cost-effective. In addition, stratification can be used to
ensure that important areas of the site are represented in the sample. However, analysis of the data is
more complicated than for other sampling designs.
The purpose of defining strata for a stratified random sample is different from the purpose of
defining strata for a scale of decision making. The strata in a stratified random sample are sampled
separately, then the data are combined to create estimates for the entire site or scale of decision
making. Stratum estimates are also available; however, decisions based on individual stratum
estimates will not have the same decision error rates as those defined in Step 6: SPECIFY LIMiTS
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ON DECISION ERRORS.
Composite Sampling
If analysis costs are high compared to sampling costs and the parameter of interest is the
mean, then the use of composite samples should be considered. Composite sampling involves
physically mixing two or more samples before analysis. This method must be used in conjunction
with a sample design in order to determine sample locations (for instance, random composite
sampling). Compositing samples can be a cost-effective way to select a large number of sampling
units and provides better coverage of the site without analyzing each unit.
Composite sampling is useful for estimating or testing the mean when information about
variability is not necessary. It is also useful if the samples are to be used as a screening device.
Additionally, since the amount of contamination in a composite sample should be larger than in an
individual sample, there are times when a contaminant may be more easily detected in a composite
sample. However, information on extreme values and variability is lost with composite data. The
population of interest must be relatively homogeneous for compositing to be feasible. Sometimes
individual samples are changed by the mixing process; for instance, volatile chemicals may evaporate.
In addition, when the action level is close to the limit of detection, the potential dilution caused by
compositing makes the use of composite sampling infeasible. Therefore, composite sampling designs
should be considered with caution.
2. STATISTICAL MODELS
Statistical models describe how the observed responses are expected to behave by relating a
measured value to the true parameter of interest and any sources of uncontrolled variation. Estimates
can then be derived for the parameter of interest and these sources of variation using the model. The
model is very important for understanding the assumptions underlying a proposed test statistic and
sampling design. Thus, it will later serve as the basis for the data quality assessment.
A statistical model consists of fixed components and random components. What is regarded
as fixed or random will be determined by the test of interest and by the inherent structure of the
survey design. Usually, the parameter of interest (for instance, a mean) is considered fixed while the
sources of uncontrolled variation are considered random. These sources include analytic/measurement
errors, temporal arid spatial components, and any other factors that may affect the data collection.
The model should:
1. Specify distributional characteristics of the random components; for instance, their means
are usually assumed to be zero and the variances are assumed to be stable.
2. Identify which components are independent of one another. This information is usually
based on historical information, pilot data, or professional judgement.
3. Specify the relationship between the various components; for instance, if they behave in
an additive or multiplicative fashion (or some combination).
4. Identify any correlation structure if temporal or spatial aulocorrelations are considered
present.
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3. CONFIDENCE INTERVALS AND HYPOTHESIS TESTS
Confidence intervals and formal hypothesis tests are two statistical methods that can be used
for decision making. A hypothesis test controls both the false positive decision error rate (cx) and false
negative decision error rate (13). A confidence interval only controls the probability of making a false
positive decision error (a) (for example, concluding that a site is clean when it is truly dirty).
However, the probability of making a false negative decision error (13) is fixed at 50% for confidence
intervals (i.e., 13 = .5).
A confidence interval and a hypothesis test can be very similar. Consider the problem of
determining whether the mean concentration (j.i) of a site exceeds a cleanup standard (CS), where the
contaminant is normally distnbuted. A confidence interval could be constructed for the mean, or a t-
test could be used to test the statistical hypothesis:
H 0 : ji > s vs. H 1 ’ ji < CS.
If the site manager’s false negative decision error rate is .5 (i.e., 13=5) then these methods are
the same. Additionally, with a fixed a. the sample size of a confidence interval only influences the
width of the interval (since 13=5). Similarly, the sample size of a t-test influences 13 and 8 (where 8 =
upper value of the gray region minus the lower value of the gray region). However, by solving for the
sample size using a t-test, one can substiiutt back into the sample size equation for a confidence
interval and compute a width corresponding to this sample size. Then the results of the two methods
will be identical.
Although the results of the hypothesis teSt and the confidence interval may be identical, the
hypothesis test has the added advantage of a power curve. The power curve is defined as the
probability of rejecting the null hypothc’.is An ideal power curve is I for those values corresponding
to the alternative hypothesis (all p CS. in ih example above) and 0 for those values corresponding
to the null hypothesis (all i> CS. in the e .imple above). The power curve is thus a way to tell how
well a given test performs, and can be u%ed to compare two or more tests. Additionally, if the null
hypothesis is not rejected, the po et cur’.e gives the decision maker some idea of whether or not the
design could actually reject the null h ,pothc is for a given level (ji).
There is no corresponding idea of a power curve in tern s of confidence intervals. To derive a
power curve, one would need to translate the confidence interval into the corresponding test (i.e., a t-
test) and then compute the power curve Additionally, whereas a statistical test accounts directly for
the false negative decision error, a confidence interval does not (13 = .5). Finally, a confidence interval
and a statistical test almost always are based on distributional assumptions, independence assumptions,
etc. If these assumptions are violated, it may be easier to select an alternative test (for example, a
non-parametric test) than it is to denve an alternative confidence interval. For these reasons, this
document concentrates its discussion on hypothesis testing.
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SECTION H: THE DQO PROCESS AND THE SUPERFUND
ACCELERATED CLEANUP MODEL
OVERVIEW OF THE SUPERFUND ACCELERATED CLEANUP MODEL
The Office of Solid Waste and Emergency Response has introduced an initiative that is
designed to streamline and accelerate Superfund cleanups. This initiative is called the Superfund
Accelerated Cleanup Model (SACM). The goals of SACM are to make hazardous waste cleanups
more timely and efficient through better planning and integration of all Superfund programs (within
existing statutory and regulatory requirements). The DQO process provides a framework for planning
field investigations under SACM.
SACM eliminates certain distinctions between the remedial and removal programs and views
them as separate legal authorities under one program: the Superfund program.’ Response actions are
divided into early actions and long-term actions based primarily on the length of time the response
action will take. Early actions can be taken under either removal or remedial authorities. Long-term
actions will be taken under remedial authority. SACM provides a streamlined approach for non-
tiniecritical removals and all remedial actions. This approach has six aspects:
• a continuous process for assessing site-specific conditions and the need for action;
• cross-program coordination of response planning;
• prompt risk reduction through early action (removal or remedial);
• appropriate cleanup of long-term environmental problems;
• early public notification and participation; and
• early initiation of enforcement activities. 2
THE ROLE OF THE DQO PROCESS IN IMPLEMENTING SACM
To produce data that can be used for multiple purposes, careful planning is required. Site
managers need to define the objectives of their field investigations and coordinate among different
existing programs (e.g., the removal, site assessment, and remedial programs). They also will need to
document planning activities well so that if the site manager or Regional Decision Team (RDT)
determines later that a further assessment or different response action is appropriate, the planning
information and data collected in the earlier field investigation can be used by others within
Superfund.
The DQO process provides a framework for planning multiple field investigations and
documenting those planning activities. The DQO process encourages the participation of all those
people involved in generating or using site data. If there is a reasonable chance that the site could
require response actions under different legal authonties (removal/remedial) or different programs
under the same authority (site assessment/remedial), then representatives from these programs are
encouraged to participate on the DQO planning team The DQO process provides a logical, step-by-
step procedure for organizing the complex issues that cut across different programs and project phases
and for keeping the team focused on the issues most relevant to planning the field investigation.
‘US EPA. Supcrfund Accelerated Cleanup Model (SACM).’ Pubbcaiion No 9203 1.01. Memo from Don R Clay. April 7. 1992, p 3.
1 OSWER Publication 9203 1.051. Status of Key 5 ,4CM Program Management Issues — Interim Guidance, December 1992. p I
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APPENDIX II
APPLICATION OF
DATA QUALITY OBJECTIVES
TO SUPERFUND SITES
EXAMPLES
SECTION A
GROUND-WATER EXAMPLE
THE WATERVILLE MUNICIPAL LANDFILL SUPERFUNI) SITE
1.0 BACKGROUND
The Waterville Municipal Landfill was in operation from 1967 to 1985. During this time, the
facility accepted residential and commercial waste. Historical information indicates that waste solvent
was disposed of at the Waterville Municipal Landfill. One chemical in particular. perchloroethylene
(PCE), was disposed of in large quantities. PCE is a class C, possible human carcinogen which
mainly targets the kidney. Ingestion and inhalation of drinking water from contaminated ground water
are considered viable exposure routes.
The Waterville Municipal Landfill is situated in the Atlantic coastal plain overlying an
unconfined aquifer that serves as a drinking water source for nearby residents via domestic wells (see
Figure A-i). Local residents are concerned that the landfill may be releasing contaminants into the
ground water. EPA has initiated an Expanded Site Investigation (ES!) because of the potential for
exposure to PCE through drinking water.
The aquifer underlying the landfill site was previously contaminated by PCE from a leaking
tank at a dry cleaning facility 1 which is hydraulically upgradient from the landfill site. The leaking
tank was removed in 1990. PCE was detected during quarterly sampling in 1991 and 1992, but was
detected below levels of concern. Well A is hydraulically upgradient from the landfill and is located
at the site boundary. Two drinking water wells — wells B and C — are within ¼ mile and are
hydraulically downgradient from the site (see Figure A-2). Any leakage from the landfill will affect
only the downgradient wells.
2.0 DQO DEVELOPMENT
The following is an example of the output from each step of the DQO process.
Step 1: State the Problem — a description of the problem and specifications of available resources
and relevant deadlines for the study.
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(I) Identify the members of the DQO scoping team — The members of the scoping team
will include the Site Assessment Manager (SAM), a field sampling expert, a chemist, a
hydrogeologist, a QA Officer, and a statistician. The SAM is the decision maker.
(2) Define/refine the conceptual site model — Figure A -I illustrates some of the main
elements of the conceptual site model, such as the source of contamination, routes of
migration, and potential receptors (humans living in households connected to the
domestic water supply fed by wells B and C). Additional information needed to
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Upgri n1
Monlteilng
WoU A
Downgr dent
Dnnklng Wat•r
Wefls B and C
__________ lb Oo’* X
£ i, j jf ii
5—
Figure A-i. Cross.section VIew of Waterville Site
Upgradient Well
Well A
‘— Property Boundary
Dowrigradierit Wells
Well B
Well C
Figure A-2. Plan View of Waterville Site
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complete the conceptual site model includes the type of contaminant (PCE) and a
range of expected concentrations.
(3) Define exposure scenario — PCE located in the landfill can be released from decaying
containers, escape from the unlined landfill, and migrate into the ground-water aquifer
which is the drinking water supply for the town. Residents may be exposed to PCE
contamination through derrnal contact, inhalation, and ingestion of drinking water
during routine daily activities in their homes, such as cooking and showering.
(4) Specify the available resources — EPA would like to take the minimum samples
necessary that would still provide adequate data quality to support a defensible
decision. There are adequate resources to collect and analyze a few samples from each
of the three wells.
(A) Time — Residents with wells near the site are concerned about the safety of
their drinking water. Local representatives would like this problem addressed
within 6 months.
(B) Identjfy project constraints — In the pre-remedial phase of the Superfund
process, financial resources are limited.
(5) Write a brief summary of the contamination problem — The Waterville Municipal
Landfill is known to have accepted large quantities of PCE, and now residents of the
town are concerned that the PCE may be leaking and contaminating their domestic
water supply via two drinking water wells located near the landfill.
Step 2: Identify the Decision — a statement of the decision that will use environmental data and the
actions that could result from this decision.
(1) State the decision — Determine whether there has been a release of PCE from the
Waterville Municipal Landfill into the drinking water aquifer of Waterville.
(2) State the actions that could result from the decision —
(a) Recommend Site Evaluation Accomplished (SEA); or
(b) Recommend further assessment or a response action.
Step 3: Identify the Inputs to the Decision — a list of the environmental variables or characteristics
that will be measured and other information needed to make the decision.
(I) Identify the informational inputs needed to resolve the decision — Concentrations of
PCE in ground water are needed from at least one upgradient location and at least one
downgradient location near the landfill.
(2) Identify sources for each informational input — The information on PCE
concentrations in ground water can be obtained through analytical measurements
performed on water samples drawn from upgradient well A and downgradient wells B
and C. There are existing data br well A gathered during 1991 and 1992.
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During 1991 and 1992, quarterly PCE data were collected from well A, the upgradient
well. The SAM is concerned that the upgradient level of PCE contamination may
have changed over the course of the sampling which began two years ago. If the
contamination problem has changed during the two years, the previously collected data
may not be appropriate and new data may need to be collected. Therefore, the SAM
needs to verify that there are no temporal trends in the data for well A. A plot of the
eight observations shows no visible trends. The SAM, however, has decided to
compare the data from 1991 and 1992 to verify that the distribution of PCE
contamination has not changed.
I Observations of PCE Concentrations (ppb) IL
Year Jan. 1 April 1 July 1 Oct. 1 Mean
Std. Dev.
Variance
1991
0.406
0.399
0.340
0.383
0.382
0.0296
8.767E-04
1992
0.434
0.347
0.422
0.383
0.397
0.0395
I.563E-03
Differences
(1991 minus 1992)
-0.028
0.052
-0.082
0.0
-0.0145
0.0559
3.124E-03
Evaluation of changes in the PCE concentration over the sampling period 1991-1992
Comparison of Sample Variance: An F-test can be used to test the uniformity of two
variances by comparing the ratio of the two variances with critical values from an F-
distribution. The ratio of 1991 and 1992 variances is:
F = l.563E-03 = 1 783
8.767E-04
Since the SAM wishes to test H 0 : = versus H 1 : & , the
critical region (with a = .1) is given by:
F < = 0.1078
F> F = 9.28
Since 1.783 0.1078 and 1.783 9.28, the SAM cannot conclude that the variance in
1991 is different from the variance in 1992. Therefore, the SAM may assume these
variances are equal.
Comparison of Sample Means: A t-test can be used to test the equivalence of two
sample means. Since it has already been concluded that the variances are not
different, a pooled t-test of the form:
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mean 1 - mean 2 .0145
______ ____ v.593
s4 .; -. + .0346 J - .4
( n 1 — 1 ) 2 +(n 2 — 1 ) s 2 2
where S = _______________
p n 1 +n 2 -2
may be used. This value will be compared to the critical value of a t-distribution with
6 degrees of freedom. Since 0.593 is less than the critical value, 1.943, the SAM
cannot conclude that the yearly means are differ ’ nt. As a result, the SAM has
determined that the sampling data from 1991 and 1992 are adequate for use in the
comparison with downgradient wells.
(3) Define the basis for establishing contaminant-specific action levels — The action level
for this problem is the lowest possible PCE concentration that demonstrates a
significant increase in comparison to the upgradient concentration.
(4) Identify potential sampling techniciues and appropriate analytic methods — The bottom
valve bailer (teflon or stainless steel 316) has been identified as a potential sampling
technique. A dedicated sampler will be used for each well. GC/MS is the proposed
analytical technique.
Step 4: Define the Boundaries of the Study — a detailed description of the spatial and temporal
boundaries of the decision; characteristics that define the environmental media, objects, or
people of interests; and any practical considerations for the study.
(1) Define the spatial boundaries —
(A) Define the domain within which all decisions must apply. The study will focus
on ground water within the unconfined aquifer below the landfill.
(B) Specify the characteristics that define the population of interest. PCE
concentrations in ground-water monitoring wells B and C. For the purposes of this
study, these wells are assumed to be representative of the aquifer below the landfill.
(C) Define the scale of decision making. Samples will be taken from the two
downgradient ground-water monitoring wells (B and C). A separate decision will be
made for each drinking water well.
(2) Define the temporal boundaries —
(A) Determine what timeframe the sampling data must represent. Because the study
is not intended to determine health risks posed by PCE, there is no specific timeframe
to which the results will apply.
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(B) Determine when to collect data. EPA is interested in characterizing the
contamination at this site quickly because of the potential adverse health effects of
exposure to PCE in drinking water. Because the data from the three wells will be
compared, samples will be collected on the same day. Past experience at similar sites
indicates that there are no systematic variations in PCE concentration over time, so
samples may be taken at any time of day.
(3) Identify practical considerations that may interfere with the study — EPA does not
expect to encounter any practical constraints while sampling.
Step 5: Develop a Decision Rule — an “if. ..then ..“ statement that defines the conditions that would
cause the decision maker to choose among alternative actions.
(I) Specify the parameter of interest — The study is trying to quickly determine whether
the downgradient concentration of PCE is significantly greater than the upgradient
concentration, so the SAM has decided to specify the parameter as an observation of
PCE concentration in each of the downgradient wells.
(2) Specify the action level for the study — The action level for this problem is the lowest
possible PCE concentration that demonstrates a significant increase when compared
with the upgradient concentration. The specific concentration will be identified during
the Optimize the Design step.
(3) Develop a decision rule (an “if...then...” statement ) — U any downgradient sample
yields a PCE value significantly greater than the upgradient well, then there is actual
contamination of the ground water and further assessment or response is required;
otherwise recommend SEA.
Step 6: Specify Limits on Decision Errors — the SAM’s acceptable decision error rates based on a
consideration of the consequences of making an incorrect decision.
(1) Determine the possible range of the parameter of interest The scoping team has
estimated the range of the parameter of interest to be 0-10 ppb PCE in the ground
water, based on the evaluation of similar PCE releases from other sites.
(2) Define both types of decision errors and identify the potential conser uerices of each —
(A) Define both types of decision errors and establish which decision error has the
more severe consequences. The two decision errors are:
Decision Error ‘a’: Decidmg that the downgradient well PCE concentration is greater
than the upgradient well when it is not. The consequences of this decision error
include the unnecessary costs of further study, and the possibility of unnecessary
remedial or emergency removal action. Treating ground water is usually a lengihy and
resource-intensive process. Other remedial options such as providing an alternate
drinking water supply can be very costly also. A positive consequence of taking
unnecessary action is that some environmental improvement may occur (e g, through
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removing very low levels of PCE and other contaminants), even though the
improvement may be of little value when compared to the costs.
Decision Error ‘b’: Deciding that the downgradient well PCE concentration is not
greater that the upgradient well when it is. Some consequences of this decision error
include environmental damage, increased future health costs, and increased cancer
illness and deaths. A positive consequence is that resources are conserved. While the
resource savings may be of small consequence when weighed against the negative
consequences, it is important to consider them here. A complete, balanced picture of
the problem can only be developed if both positive and negative consequences of the
decision error are considered. Decision Error ‘b’ is the more severe decision error.
(B) Establish the true state of nature for each decision error. The true state of nature
for decision error ‘a’ is that the downgradient well does not have a higher
concentration of PCE than the upgradient well. The true state of nature for Jecision
error ‘b’ is that the downgradient well has a higher concentration of PCE than the
upgradient well.
(C) Define the true state of nature for the more severe decision error as the baseline
condition (null hypothesis) and define the true state of nature for the less severe
decision error as the alternau ye hypothesis.
Null hypothesis, H 0 = The downgradient well has a higher concentration of PCE than
the upgradient well.
Alternative hypothesis. H The downgradient well does not have a higher
concentration of PCE than the upgradient well.
(D) Assign the ternu Tf I;i pvsi::ve” and “false negative” to the proper errors.
False positive error = decision error
False negative error = decision error ‘a’
(3) Identify Acceptable Decision Error Rates —
False Positive Error: If the downgradient concentration of PCE is greater than the
upgradient concentration due to a release, the SAM desires at least a 95 percent
probability of finding that a release has occurred (5% probability of a false positive
error). In this example, the SAM becomes increasingly concerned the higher the
downgradient PCE concentration is in comparison to the upgradient well.
False Negative Error: If there truly has been no release, the SAM wants at most a 5
percent probability that the data indicate a release.
(4) Specify the Gray Region — There will be no gray region for this problem since the
decision is to determine a “significant difference’ between the concentration of the
downgradient wells and background concentrations rather than a fixed point (action
level).
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Step 7: OptimIze the Design — the decision maker will analyze existing data and select the lowest
cost sampling design that is expected to achieve the DQOs.
(1) Develop general sampling and analysis design alternatives — Existing data from well
A were found to be useful in determining the contamination level upgradient of the
Site. New data will be generated for the dowagradient wells and tested to determine
whether they belong to the same population as the upgradient data. If the
downgradient values arc significantly higher, then it will be concluded that the
upgradient and downgradient concentration levels come from different populations.
An upper 95% tolerance limit on the population (with 95% probability that at least
95% of the distribution wtll be less than the limit) will be used to make this
determination.
A tolerance interval may be used to prove that a well is contaminated; however, it
cannot conclusively determine that a well is not contaminated; The scoping team
believes, based on the past history of the site, that wells B and C are contaminated.
ThCs, a tolerance interval will be used to quickly verify that the wells are
contaminated. If data from wells B and C fail to exceed the upper tolerance limit,
then this method is inconclusive and an alternative sampling design should be
developed.
The tolerance interval used will be based on a normal distribution. Hence, the
assumption that the eight observations from well A follow a normal distribution should
be tested. Due to the small sample size, Gearys Test for Normality will be used to
test this assumption. The test statistic will be
Yk - .
In - (E’) 2 ’ )
and an approximate test for normality will be
z = ( a — 0.7979)
0.2l23 N(0,1)
If Z> 1.96, the assumption of normality at a 5% level of significance will be rejected
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For the data from well A,
0.248829
a • ___________ 0.835914
%18 0.007739
z ( 0.835914 - 0.7979 ) = 0.506459
0 ,2123
Since Z < 1.96, the idea that the data are normally distributed cannot be rejected.
Therefore, it will be assumed that the upgradient data are normally distributed and can
be used to construct a tolerance interval.
Using the eight observations from well A, an upper tolerance interval (TL) can be
constructed by:
TL = mean + K * Std. Dev.
where K is a one-sided normal tolerance factor. A table of tolerance factors can be
found in the Guidance Document on the Statistical Analysis of Ground-water
Monitoring Data at RCRA Facilities, EPA, 1993. In this case, K(0.95, 0.95, 8) =
3.188, and
TL = 0.389 + 3.188 * 0.03325 = 0.495
Any one observation over 0.495 will cause the SAM to conclude that additional
contamination above the upgradient level has been observed. In other words, any one
observation from either downgradient well that exceeds 0.495 will be cause for
deciding that there has been a release from the landfill.
Statistical Models
For each observation y 1 from the upgradient well A,
y, = p + e 1
where p represents the mean PCE concentration for the upgradient well and the e,’s
represent sampling and measurement error which are assumed to be distributed with a
mean of 0 and a variance equal to 2. Unless the data demonstrate otherwise, the
observations from the downgradient wells B and C should also follow this model.
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Sample Size
Ideally the SAM would like to collect just one sample from each of the two
downgradient welts. Collection of one additional sample from the upgradient well is
recommended to ensure that the direction of the plume from the dry cleaning facility
has not changed.
(2) Select the most resource-effective design that satisfies all of the DOOs — This design
is resource-effective because it requires a small number of samples (one from each
well). However, if neither sample exceeds 0.495. then an alternative sampling design
will be developed which would satisfy the scoping team’s limits on decision errors.
(A tolerance interval will only satisfy the limits of a false-positive error.)
(3) Document the details arid assumptions of the selected design — This design assumes
that the purpose of sampling is to verify that a release has occurred. If the data do not
demonstrate that a release has occurred, the decision maker cannot conclude that the
wells are not contaminated and an alternative sampling design will be developed.
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SECTION B
REMOVAL PROGRAM EXAMPLE
THE LEADBURY SUPERFUN1) SITE
1.0 BACKGROUND
The Leadbury Superfund Site covers a large area ir two counties within the State of
Oklahoma. The soil within this area has elevated levels of lead. The site surrounds the town of
Leadbury where the Lead Smelter Co. has been mining and smelting lead since 1933. Currently, the
area of surface soil contamination extends for approximately 36 square miles surrounding the town.
The lead has allegedly onginated from stack emissions or possibly from improper disposal of waste
materials from the smelting and mining processes. Lead concentrations exceed 500 ppm at some
portions of the Site.
The Environmental Protection Agency (EPA) has decided to conduct the Remedial
Investigation/Feasibility Study (RIIFS) and the remedial design for this site concurrently with the
removal action in observance of the Superfund Accelerated Cleanup Model (SACM) guidance.
Therefore, all data collected during L’ e rcmoal phase will be used in later phases of the study.
The predominant threat to the public from this site comes from the inhalation and/or ingestion
of lead-contaminated soil particles Lead is kitown to produce many adverse health effects in humans
ranging from reproductive system disorders. cklays in neurological and physical development,
cognitive and behavioral changes, and uKrea.cd blood pressure. The main exposure pathway for lead
is inhalation. Inhalation exposure is most ttkcl to occur during dry and windy conditions that are
prevalent dunng the summer months Children are at special risk from lead exposure because their
behavior traits result in greater intake of soil per body weight. In addition, children are more likely
than adults to have nutnent deficiencies which increase the metal absorption and retention. It has also
been indicated that adverse neurological effects occur at lower blood lead level thresholds in children.
An Emergency Removal Branch (ERS) assessment of the site was conducted in two phases.
During Phase I, an area of 36 miles surrounding the town was sampled to determine the contaminants
of concern. The samples were analyzed for 24 target compound metals and the results identified lead
as the contaminant that should be addressed in more extensive sampling. In Phase II, additional
surface soil locations were sampled within the Phase I area from 53 locations that were determined to
be “high-access” areas for children, the target population at risk. These included school yards,
playgrounds, day care centers, and church yards. Twenty-six of the high-access areas were determined
to have concentrations of lead in excess of the removal program’s action level of 500 ppm. These 26
areas were considered to present imminent and substantial endangerment to the public.
As part of the sampling done in Phase II, the removal program determined that the lead
contamination was distributed bimodally (i.e., a graph of the distribution of lead concentrations shows
two distinct peaks). The concentration of the low mode is 30 ppm while the concentration of the high
mode is 700 ppm. The lower concentration of lead is thought to have come from aerial deposition
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associated with the lead smelter and other mining operations. The higher concentrations are thought to
be due to the use of contaminated fill material. The fill most likely came from mining tailings. It was
therefore decided that a sampling plan should be initiated to locate the portions of the high-access
areas that had lead contamination in excess of 500 ppm. The contaminated soils would then be
removed and clean fill would replace it. The removal program has decided to use the DQO Process to
help them develop the sampling plan to locate areas of excess lead contamination.
As a precursor to the DQO Process, the ERB estimated the cost of disposal for the
contaminated soil. They subjected soil samples to the Toxicity Characteristic Leaching Procedure
(TCLP) to determine if the contaminated soil was considered a “hazardous substance” under RCRA
regulations and would therefore need to be disposed of at a more expensive hazardous waste facility.
The tests showed that the contaminated soil was considered non-hazardous and could therefore be
disposed of at a less costly municipal landfill.
2.0 DQO DEVELOPMENT
Step 1: State the Problem — a description of the problem(s) and specifications of available
resources and relevant deadlines for the study.
(1) Identify the members of the DQO scoping team — The members of the scoping team
will include the On-Scene Coordinator (OSC), the manager of the Lead Smelter Co., a
Quality Assurance Officer, a representative of the Leadbury town council, a statistician
who has experience with sampling design, and a chemist with field experience. The
decision maker will be the OSC of the removal program.
(2) Define/refine the conceptual site model — The source of contamination is
from lead found in surface soil at 26 Thigh-access” areas around the city. The
lead has been deposited through air deposition at the high-access areas from
lead smelter operations in the region over a period of 60 years. The
concentration of lead is expected to be from 0 - 1000 ppm based on site
preliminary site investigations. The receptors are children between the ages of
1-12 years.
(3) Define the exposure scenario — EPA is concerned about the secondary source of lead
contamination existing in the surface soil at 26 high-access areas throughout the city,
so the original release mechanism from the smelter is not directly relevant. However,
lead will be released from the surface soil in the form of dust. The lead will be bound
to soil particles. Children will be exposed through inhalation of the dust particles and
through ingestion of contaminated soil at each site. The future land use is assumed to
be the same as the current mixed uses.
(4) Specify available resources — The total budget for sampling, removal, and disposal is
$5,560,000. Therefore approximately $200,000 is available for each of the 26 high-
access areas.
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(A) Time. All removals should be completed within 6 to 8 months.
(B) Identify project constraints. The OSC has requested that all stages of the operation
be performed in a manner that minimizes the time and cost of sampling, analysis, and
disposal,
(5) Write a brief summary of the contamination problem — Surface soil in high-access
areas of Leadbury are contaminated with relatively high concentrations of lead. EPA
needs to determine what portions of soil within the high-access areas need to be
removed.
Step 2: Identify the Decision — a statement of the decision that will use environmental data and the
actions that could result from this decision.
(1) State the decision(s ) — Determine what areas within the 26 high-access areas have
concentrations of lead in the soil that exceed the removal program’s regulated
standard.
(2) State the actions that could result from the decision —
(a) Further study will take place to delineate contamination, the surface soil will
be removed, and clean fill will replace it.
(b) The surface soil will be left intact.
Step 3: Identify the Inputs to the Decision — a list of the environmental variables or characteristics
that will be measured and other information needed to make the decision.
(1) Identify the informational inputs needed to resolve the decision — Concentration of
lead in the soil within the 26 high-access areas.
(2) Identify sources for each informational input — The concentration of lead can be
measured from soil samples.
(3) Define the basis for establishing contaminant-specific action levels — The action level
for lead in soil has been set for the removal program by the Agency for Toxic
Substance Disease Registry (ATSDR), based on the risk of exposure and the
possibility of adverse health consequences. The action level is 500 ppm.
(4) Identify potential sampling techniques and appropriate analytic methods — The
analytical method will be atomic absorption. The tulip bulb planter has been identified
as a potential sample collection device.
Step 4: Define the Boundaries of the Study — a detailed description of the spatial and temporal
boundaries of the decision; charactenstics that define the environmental media, objects, or
people of interest; and any practical considerations for the study.
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(I) Define the spatial boundaries —
(A) Define the domain within which all decisions must apply. The boundaries of the
study will be limited to the property boundaries of each separate high-access area that
has been identified as having soil contamination that exceeds the removal program
standard of 500 ppm for lead. Each of the 26 high-access areas will be evaluated and
sampled separately.
(B) Specify the characteristics that define the population of interest. Surface soil (0-6
inches) associated with the site. Each of the 26 high-access areas will be considered
subpopu lations.
(C) Define the scale of decision making. Because the contaminated soil is thought to
come from fill material, the sampling plan should be adequate to detect the smallest
area that would reasonably have been filled within the high-access areas. The scoping
team has chosen a circle with a diameter of 40 feet to a depth of 6 inches to represent
the area that corresponds to the smallest area that could reasonably have been filled.
This is the area that corresponds to four dump truck loads (8 tons) of fill material,
spread 6 inches thick. Therefore the sampling plan must adequately detect
contaminated circular areas of contaminated soil that have a diameter of 40 feet.
(2) Identify temporal boundaries — The EPA is facing public pressure to reduce the
exposure risks from the site quickly.
(A) Determine what timeframe the sampling data must represent. Because the study
is not intended to determine risk, there is no specific timeframe to which the results
will apply.
(B) Determine when to sample. Lead in soil is stable. It will not degrade or migrate
from the ‘high-access areas”. Therefore lead can be sampled at any time. For best
results, soil samples should be taken when the soil moisture is relatively low (less than
30%) so that the core samples will hold their form.
(3) Identify practical considerations that may interfere with the study — Two of the high-
access areas provide a passageway between elementaiy school buildings. For students
to avoid possible exposure, a walkway built of plywood will be installed.
Additionally, it will not be possible to perform removals on these areas during regular
school hours (8:00 am- 2:30 pm).
Step 5: Develop a Decision Rule — an “if...then...” statement that defines the conditions that would
cause the decision maker to choose among alternative actions.
(1) Specify the parameter of interest — A hot spot can be considered as a maximum
concentration. Therefore the parameter of interest is the maximum concentration.
(2) Specify the action level for the study — The removal program’s action level for lead
in soil is 500 ppm. The action level has been set by the ATSDR.
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(3) Develop a decision nile (an “if...then...” statement ) — If the maximum concentration
of lead in any high-access area is greater than 500 ppm, then a second round of
sampling will be implemented to delineate the extent of soil contamination.
Otherwise, no action will take place.
Step 6: Specify Limits on Decision Errors — the decision maker’s acceptable decision error rates
based on a consideration of the consequences of making an incorrect decision.
(1) Determine the possible range of the parameter of interest — The possible range of lead
concentrations is expected to be from 0-1000 ppm.
(2) Define both types of decision errors and identify the potential consequences of each —
(A) Define both types of decision errors and determine which decision error has the
more severe consequences. The two decision errors are:
Decision Error ‘a’: Determining that circular areas of contaminated soil with a radius
of 40 feet or greater do not exist when they actually do; i.e., determining there are no
hot spots when a hot spot actually exists. The consequence of this error is that
contaminated soil will not be removed and human health will be endangered. Decision
Error ‘a’ is the more severe decision error.
Decision Error ‘b’: Determining that the soil is contaminated when in reality it is not;
i.e., determining that a hot spot exists when in reality there are no hot spots. The
consequence of this error is that time and energy will be spent on additional sampling.
The public will view this error positively in that it shows that the overriding concern is
for protecting human health. The consequences, therefore, are far less severe than the
consequences of the other decision error.
(B) Establish the true state of nature for each decision error. The true state of nature
for decision error ‘a’ is that a hot spot exists. The true state of nature for decision
error ‘b’ is that there are no hot spots.
(C) Define the true state of nature for the more severe decision error as the baseline
condition or null hypothesis and define the true state of nature for the less severe
decision error as the alternative hypothesis.
Null Hypothesis, l-L = A hot spot exists. (The concentration of an individual sample is
above 500 ppm.)
Alternative Hypothesis, H A hot spot does not exist. (The concentration of an
individual sample is less than 500 ppm.)
(D) Assign the terms ‘7zlse positive” and “false negative” to the proper errors.
False positive error = decision error ‘a’
False negative error = decision error ‘b’
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Specify the Gray Region — The scoping team has set the gray region, which spans 100 ppm, to the
left of the action level.
(4) Identify Acceptable Decision Error Rates —
(a) False Positive Error: The scoping team can accept a rate of 20% for the
probability of a false positive (see Figure B-I).
(b) False Negative Error The scoping team has set the acceptable rate of making
a false negative error at 30% (see Figure B-i).
Figure B!. Design Performance for Soil Lead Testing
Step 7: Optimize the Design — the decision maker will select the lowest cost sampling design that
is expected to achieve the DQOs.
(I) Develop general sampling and analysis design alternatives — For each design
alternative, the statistician must formulate a statistical model (i.e., a mathematical
expression) that tests the hypothesis and select the optimal sample size that satisfies
the decision maker’s limits on decision errors.
u)
28
a.
F
Th e Concentration of Lead (ppm)
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A search sampling method using systematic (or grid) samples will be used to
determine whether or not a “hot spot” of contamination exists. If the concentration ot
lead in any sample within the boundaries is significantly greater than 500 ppm, then a
second round of sampling will be implemented to determine the extent of soil
contamination. Otherwise, no action will take place.
The second round of sampling, sequential sampling, will characterize the extent of the
area that requires removal. Additional soil samples will be taken at a point one-half
the distance to the next non-contaminated sampling point. If any sample in the second
round is contaminated, additional samples will continue to be collected one-half the
distance to the nearest non-contaminated sampling point until a sample shows no
contamination. Once this occurs, contaminated soil will be removed up to and
including the last clean sample. The soil wiLl be removed to a depth of 8 inches
because this is the maximum depth that children are expected to receive exposure from
soil during normal activity. Clean fill will be used to fill the depressions made during
removal activity.
Samples will be taken in a triangular-shaped grid pattern. The distance between
samples will be 42.5 feet (see Figure B-2). Six-inch core samples will be taken at the
grid nodes, homogenized, and analyzed at each sampling location.
Because of the extreme bimodal distribution of the lead concentration, the design
assumes that when a hot spot is sampled, it will not be mistaken for background and
vice versa.
Statistical ModeLs
For each observation y:
y, = V 1 +
where v 1 = true value of the th observation and
e 1 = sampling error for the i. observation.
The e 1 ’s are independently and identically distributed with the mean equal to 0 and
variance equal to o .
Sample Size
Below is an explanation of a procedure that is used to determine the number of
samples needed to detect hot spots of contamination within a pre-specified confidence
limit. The procedure employs three common sampling patterns (square, rectangular,
and triangular) to determine the optimal sample spacing and distance between samples.
To determine the minimum spacing between samples that will detect an elliptical hot
spot of a pre-specified size and shape with a specified confidence, the following
procedure is used:
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Sampling Plan for Representative High Access Area - School Playground
I 1300’ I I
1 22
300 ___________________
— Samples are collected
at gnd nodes
Grid Notes Triangular Sampling
Grid
G
_\,/‘ “ G Spacing betwoenj
lines. For this example
G 425ft.
Figure B-2. Triangular Sampling Grid Used to Detect Soil Lead Contamination in a
300’ x 300’ School Playground
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(A) Specify the length (L) of the long axis of the hot spot ellipse: L = 20 ft.
(B) Specify the length (R) of the short axis of the hot-spot ellipse: R = 20 ft.
(C) Divide the length of the short axis by the length of the long axis. The solution,
5, is called the shape:
Length of the short axis of the hot-spot ellipse
- =1
Length of the long axis of the hot-spot ellipse
(D) Specify the acceptable probability of finding the hot spot. in our example the
probability of not finding the hot spot corresponds to 13 = .2. (In this case, a false
positive error.)
(E) Determine the distance between samp’es (0) using the nomograph (see Figures 2-
3 and 2-4) to meet the constraints specified in the first four steps. For a square
playground area with a size of 300 ft. x 300 ft., the distance between samples and the
number of samples needed to meet the DQOs will be:
Using a square sampling pattern, 0 = 39.2 feet : 64 samples.
Using a triangular sampling pattern, 0 = 42.5 feet : 49 samples.
(2) Select the most resource-effective design that satisfies all of the DQOs — Sampling
costs include both the cost of collecting and analyzing samples. Each soil sample
tested for lead will cost $75.00. The total cost of sampling will depend on the total
number of samples.
(3) Document the details and assumptions of the selected design —
• The target (hot spot) ts circular. For subsurface targets, this applies to the
projection of the target to the surface.
• Samples or measurements are taken on a triangular grid.
• The distance between grid points is much larger than the area sampled, measured,
or cored at grid points — that is, a very small proportion of the area being studied
can actually be measured.
• The definition of “hot spot” is clear and unambiguous. This definition implies that
the types of measurement and the levels of contamination that constitute a hot spot
are clearly defined.
• There are no measurement misclassification errors — that is, no errors are made in
deciding when a hot spot has been hit.
The most efficient sampling plan is one that uses a triangular sampling grid (see
Figure B-2) because it meets the constraints of the DQOs with the fewest number of
samples and therefore has the lowest total cost.
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1.00
Figure B-3. Curves relating hG to consumer’s uncertainty, , for different target shapes
using a square grid (from Zirschky and Gilbert 1984, with permission)
0.60
0.40
Curves relating L/G to consumer’s uncertainty, [ , for different target shapes
using a triangular grid (from Zirschky and Gilbert 1984, with permission)
0.80
0.60
0.40
0.20
0.00
0.00 0.10 0.20 0.30
LIG
0.40 0.50 0.60 0.70 0.80 0.90 1.00
1.00
0-Ba
Figure B-4.
0.20
0.00
0.00 0.10 0.20 0.30 0.40 0.50 0.60 0.70 0.80 0.90 1.00
LIG
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SECTION C
REMEDIAL PROGRAM EXAMPLE
THE RAWHIDE SUPERFUND SITE
1.0 BACKGROUND
The Rawhide Superfund Site is a former leather tannery. Between 1982 and 1985, tannery
waste sludge was landfarrned over part or all of a 29-acre pasture (see Figure C-I). “Landfarming”
refers to a process of waste disposal that involves spraying or pouring waste onto the soil and then
disking the waste into the soil. At this site, the sludge containing high levels of chromium compounds
was disked into the soil to a depth of approximately 8 inches. Historical site information indicates that
several portions of the landfarm area have received little or no waste.
High concentrations of chromium III and VI have been detected in surface soil samples at the
landfarm. This may indicate that wastes s ere dumped on the ground, but not disked into the soil.
Ground-water sampling in wells and springs within three miles of site have shown the presence of
chromium and lead at levels below ma imum contaminant levels (MCLs). Due to the high levels of
chromium in the surface soil, the site has been placed on the National Priorities List (NPL).
The site is currently used to graze cank Several residences are located adjacent to the site.
Potential human exposure routes identiried by the site risk assessor include ingestion and inhalation of
soil particulates and ingestion of ground ater Chromium VI compounds are suspected human
carcinogens through the inhalation path a’ only Chromium 111 compounds are not considered
carcinogenic. Direct contact with chromium compounds can cause a hypersensitivity reaction.
The scoping team has decided to employ the DQO process to help them determine if there are
any areas of the landfarrn that pose an un3cccplable nsk to human health and the environment and
thus require further assessment or a response action. By using the DQO process, the team plans to
generate a statistically valid sampling design. generate results of known confidence, make defensible
decisions, and save time and resources
2.0 DQO DEVELOPMENT
Following is an example of the output from each step of the DQO process.
Step 1: State the Problem — a description of the problem(s) and specifications of available
resources and relevant deadlines for the study.
(1) Identify the members of the DQO scopin team — The members of the DQO scoping
team include the RPM, a field sampling expert, a chemist, an engineer, a risk assessor,
a QA Officer, a hydrogeologist, a DQO facilitator, and a statistician. The RPM is the
decision maker.
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(2) Define/refine the conceptual site model — The source of the contamination is from
landfarming waste disposal operations at a former leather tannery. High concentrations
of chromium have been observed in soil associated with the site. Chromium and lead
were detected in ground-water samples at levels below the MCLs. Contaminants are
migrating from surface and subsurface soils to ground water. Contaminants may also
become airborne primarily due to wind. The receptors are humans of all ages who live
within a 2-mile radius and who derive their drinking water from ground-water wells
which are connected to the ground-water aquifer below the site. Cattle who graze on
the site are also potential receptors.
(3) Define exposure scenarios — The source of the contamination is the chromium-
contaminated soil and the ground water associated with the site. Contaminants will be
released through aerial transport and migration to ground water. Contaminants may
also migrate through ground water to drinking water wells. The chromium will be
bound to soil dust particles or dissolved in ground water. The exposure routes include
ingestion of soil, inhalation of dust particles, and ingestion of ground water. The
potential exposure points are the contaminated soils on-site and houses connected to
drinking water supply. The land use for the Site LS residential.
Figure C-i. Site Map of Rawhide Superfund Site
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(4) Specify the available resources — EPA is concerned about the cost of extensive
sampling and analysis, but adequate data quality is a priority. EPA has allocated the
funds necessary for a sampling crew of four people for only one week. All sampling
must be done within that week.
(A) Time. The RPM wants this site addressed in a “reasonable timeframe.” The
RPM expects data validation to be the most time-consuming aspect of data generation.
It may take up to three months after samples are collected before the data are
available.
(B) !dentjfy project constraints. The sampling team has a limited amount of time to
collect samples due to budget constraints. This will be a major consideration during
the development of the sampling and analysis design.
(5) Write a brief summary of the contamination problem — This site was placed on the
NPL due to the discovery of chromium contaminated soil. Chromium was also
detected in ground water associated with the site which is hydraulically connected to
drinking water wells. Residents in the area can be exposed to contaminants in soil and
ground water via ingestion. Residents can also be exposed to contaminated
particulates via inhalation. The site manager has designated the soils associated with
the site as an operable unit. Since the site is on the NPL. a remedial investigation will
be performed to determine which areas of the soil pose an unacceptable risk to human
health or the environment and require further assessment or a response action.
Step 2: l [ dentify the Decision — a statement of the decision that will use environmental data and the
actions that could result from this decision.
(1) State the decision(s ) — Determine whether sections of the landfarm (soil) pose an
unacceptable risk to human health or the environment or whether they exceed ARARs.
(2) State the actions that could result from the decision —
(a) No action.
(b) Recommend further assessment or a response action.
Step 3: Identify the Inputs to the Decision — a list of the environmental variables or characteristics
that will be measured and other information needed to make the decision.
(1) Identify the informational inputs needed to resolve the decision — Surface soil
samples need to be taken within the site boundaries.
(2) Identify sources for each information input — Total chromium will be measured in
soil samples.
(3) Define the basis for establishing contaminant-specific action levels — Since a health-
based non-carcinogenic value (600 ppm of total chromium) is lower than the risk-
based carcinogenic PRG of 700 ppm for hexavalent chromium, the total chromium
concentration value is considered more protective.
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(4) Identify potential sampling techniques and appropriate analytic methods — A soil
coring device has been identified as the potential sampling technique. Atomic
absorption is the proposed analytical methodology.
Step 4: Define the Boundaries of the Study — a detailed description of the spatial and temporal
boundaries of the decision; characteristics that define the environmental media, objects, or
people of interests; and any practical considerations for the study.
(I) Define spatial boundaries —
(A) Define the domain within which all decisions must apply. Surface soil is defined
as the top 12 inches of soil within the geographic boundaries of the 29-acre landfarm
area, excluding forested areas where landfarming and disposal could not have taken
place.
(B) Specify the characteristics that define the population of ânterest. Chromium
concentrations in soil samples.
(C) Define the scale of decision making. Although the area is rural, future residential
development is possible. Residential land use represents a reasonable worst-case
scenario. The entire site h&s been divided into square areas that are approximately 200
x 200 feet. These areas are approximately one acre in size and correspond to the
expected residential lo size These areas are referred to as “exposure units” (EUs).
EUs which overlapped the site boundaries were combined with EUs having forested
areas so that 20 EUs of appro imately one acre would result. A separate decision will
be made for each EU
(2) Identify temporal boundaries — EPA is facing public pressure to reduce the exposure
risk from the site quickJ
(A) Dezennine what tune frame the sampling data must represent. Because chromium
is not migrating or degriding to any significant degree, the sampling results will apply
to lifetime exposure.
(B) Determine when so collect data. Sampling must occur within a one-week period
when EPA has made funds available.
(3) Identify practical considerations that may interfere with the study — The Center of
each EU will be marked with a wire flag. Because the site is currently used for
grazing, there is considerable concern that the cows will ingest the wire flags. This
would injure the cows and impede timely sample collection. Some background
investigation has indicated that it is not likely the cows will eat the wire flags. As a
precaution, the farmers will be informed of the sampling activities in order to protect
the welfare of the cows.
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Step 5: Develop a Dccislon Rule — an “if..,then...” statement that defines the conditions that would
cause the decision maker to choose among alternative actions.
(1) Specify the parameter of interest — The mean concentration of total chromium within
each EU will be compared to the action level.
(2) Specify the action levet for the study — The action Level for this problem wilL be 600
ppm of total chromium.
(3) Develop a decision rule (an “if...then” statement ) — If the average total chromium
concentration in the surface soil of an EU exceeds 600 ppm, then recommend further
assessment or a response action will be taken. Otherwise, no action will be taken.
Step 6: Specify Limits on Decision Errors — the decision maker’s acceptable decision error rates
based on a consideration of the consequences of making an incorrect decision.
(1) Determine the possible range of the j,ararneter of interest —The possible range of
chromium concentrations is 0-1000 ppm.
(2) Define both types of decision errors and identify the potential consequences of each —
(A) Define both types of decision errors and establish which decision error has the
more severe consequences.
The two decision errors are:
Decision Error ‘a’: One decision error occurs when the decision maker decides an EU
is not contaminated when, in truth, the mean concentration of chromium is greater than
or equal to 600 ppm. If an EU that poses an unacceptable risk is not remediated,
some resources may be saved, but this would be at the cost of increased human health
and/or environmental risk. Increased future health costs or cancer deaths may also
result. This decision error is more severe.
Decision Error ‘b’: The other decision error occurs when the decision maker decides,
based on the data, to take action when, in truth, the mean concentration of chromium
is less than 600 ppm. One possible consequence of this decision error is unnecessary
further study in the EU. This would result in wasted resources and time. Offsetting
this to some degree would be the marginal reduction in health risk if a response action
is taken.
(B) Establish the true state of nature for each decision error. The true state of nature
for decision error ‘a’ is that the mean concentration of chromium is greater than 600
ppm. The true state of nature for decision error ‘b’ is that the mean concentration of
chromium is less than 600 ppm.
(C) Define the true state of nature for the more severe decision error as the baseline
condition or null hypothesis anti define the true state of nature for the less severe
decision error as the alternative hypothesis. The hypothesis test is stated as:
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Null Hypothesis (H1): Mean concentration in the EU 600 ppm
Alternate Hypothesis (H 1 ): Mean concentration in the EU < 600 ppm
(D) Assign the terrn.s 7aLse positive” and 7alse ne azive” to the proper errors.
false positive error = decision error ‘a’
false negative error = decision error ‘b’
(3) Specify the Gray Region — The gray region corresponds to the area where the
decision maker considers the consequences of making a false negative decision error to
be relatively minor. In this example, the gray region is set to the left of the action
level between 500 ppm and 600 ppm (see Figure C-2).
(4) Identify Acceptable Decision Error Rates — The decision maker specified the
probability of deciding to take action at four different total chromium concentrations.
True Concentration of Total Chromium
Acceptable Probability of Taking Action
100 ppm
less than or equal to 1%
250 ppm
less than or equal to 10%
500 ppm
less than or equal to 25%
600 ppm
greater than or equal to 95%
Based on the above table, at a true mean of 100 ppm, the decision maker can tolerate
making a false negative decision error 1% of the time. At 600 ppm (the action level),
the decision maker wants to be confident of taking action 95% of the time (i.e.. can
tolerate making a false positive decision error 5% of the time).
Step 7: Optimize the Design — the decision maker(s) will select the lowest cost sampling design
that is expected to achieve the DQOs.
(1) Develop general sampling and analysis design alternatives — For each design
alternative, the statistician must formulate a statistical model (i.e., a mathematical
expression) that tests the hypothesis and select the optimal sample size that satisfies
the decision maker’s limits on decision errors.
Several alternate designs were discussed and subsequently deemed impractical by the
decision maker. One design was considered possible, however. A spatially intensive
design was developed which would gather composite soil samples from each EU.
Samples will be taken using a systematic grid. The sampling crew is more
comfortable with this type of design than with a random sampling plan. An
approximate t-test is suggested for each EU by calculating
600 - MA
1=
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where M b is the mean of the hth EU and v is the pooled within•EU variance. This will
be compared with the critical value of a t-distribution for C t = 0.05 and 20 degrees of
freedom. If the computed value exceeds the critical value, the null hypothesis will be
rejected.
Estimate of Variance
A limited field investigation was conducted in order to develop an estimate of the
expected variability of the contaminant. A preliminary estimate of the total standard
deviation of the chromium is 65.70 ppm.
Statistical Model
The model proposed for the observed composite sample concentrations is
= I, +
where: x,, = j ’ composite sample of the 1 th EU
= mean concentration of the 1 th EU
= deviation from p , for th composite sample of the th EU
and the C’s are distributed normally with mean zero.
095
I C>
C
. U
OC
‘-0
0 .C5
001
700
Ac oii Level
True Mean Concentration of Cr in EU (ppm)
Figure C.2. Design Performance Goal for Rawhide Site
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Sample Size
A maximum of nine samples per composite can be realistically handled. Using this
information arid the prior estimate of the standard deviation, two composite samples of
nine scoops each will be randomly selected from each of the 20 EUs. This sample
size will provide 20 degrees of freedom, provided that the within-EU variances can be
pooled.
(2) Select the most resource-effective design that satisfies all of the DOOs — Composite
samples save money by reducing analysis costs, which is important for the initial study
as well as for the next phase of study.
This design meets the decision maker’s objectives for adequately identifying which
EUs require further study or a response action. This is critical given the expected high
cost of remediation.
(3) Document the details and assumptions of the selected design — Two composite
samples of nine scoops each will be selected within each EU. A systematic grid with
nine nodes will be used to collect the first composite sample. The second composite
sample will consist of nine samples that are offset from the original grid nodes.
Within each EU it is assumed that the variance is the same, regardless of the level of
contamination. This assumption can be tested after the data are collected.
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APPENDIX III
GLOSSARY
GLOSSARY OF TERMS
action level: the numerical value that causes the decision maker to choose one of the alternative actions
(e.g., compliance or noncompliance). It may be a regulatory threshold standard, such as a
Maximum Contaminant Level for drinking water, a risk-based concentration level, a technological
limitation, or reference-based standard.
bias: the systematic or persistent distortion of a measurement process which causes errors in one direction
(i.e., the expected sample measurement is different than the sample’s true value).
boundaries: the area or volume (spatial boundary) and the time period (temporal boundary) to which the
decision will apply. Samples are collected within these boundaries to be representative of the
population of interest for the decision.
Data Quality Assessment (DQA): a process of statistical and scientific evaluation that is used to assess
the validity and performance of the data collection design and statistical test, and to establish
whether a data set is adequate for its intended use.
Data Quality Objectives (DQOs): qualitative and quantitative statements derived from the outputs of
each step of the DQO Process which specify the study objectives, domain, limitations, the most
appropriate type of data to collect, and specify the levels of decision error that will be acceptable
for the decision.
Data Quality Objectives Process: a Quality Management tool based on the Scientific Method and
developed by the U.S. Environmental Protection Agency to facilitate the planning of
environmental data collection activities. The DQO Process enables planners to focus their
planning efforts by specifying the use of the data (the decision), the decision criteria (action level),
and the decision maker’s acceptable decision error rates. The products of the DQO Process are
the DQOs.
decision errors:
raise positive error — The false positive error occurs when data mislead a decision maker into
believing that the burden of proof in a hypothesis test has been satisfied, so that the null
hypothesis is erroneously rejected. A statistician usually refers to the false positive error as alpha
(a), the level of significance, the size of the critical region, or a Type I error.
false negative error — The false negative error occurs when data mislead the decision maker into
wrongly concluding that the burden of proof in a hypothesis test has not been satisfied so that the
null hypothesis is accepted. A statistician usually refers to this as beta ( 3), or a Type II error. It
is also known as the complement of Power.
ill
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defensible: the ability to withstand any reasonable challenge related to the veracity or integrity of
laboratory documents and derived data.
directed sampling: see judgmental sampling.
gray region: an area that is adjacent to or contains the action level, and where the consequences of
making a decision error are relatively small.
judgmental sampling: a subjective selection of sampling locations based on experience and knowledge
of the site by an expert.
limits on decision errors: the acceptable decision error rates established by the decision maker.
Economic, health, ecological, political, arid social consequences should be considered when setting
limits on decision errors.
mean: the arithmetic average of a set of values.
measurement error: the difference between the true or actual state and that which is reported from
measurements.
median: the middle value for an ordered set of n values; represented by the central value when n is odd
or by the average of the two most central values when n is even.
medium: a substance (e.g., air, water, soil) which serves as a carrier of the analytes of interest.
natural variability: the variability that is inherent or natural to the media, objects, or people being
studied.
parameter: a numerical descriptive measure of a population.
percentile: a value on a scale of 100 that indicates the percentage of a distribution that is equal to or
below it.
population: the total collection of objects or people to be studied and from which a sample is to be
drawn.
power curve: the probability of rejecting the null hypothesis (HG) over the range of the population. The
power function is used to assess the goodness of a test or to compare two competing tests.
probabilistic sampling: a random selection of sampling locations that allows the sampling results to be
extrapolated to an entire site (or portion of the site).
quality assurance (QA): an integrated system of management activities involving planning, quality
control, quality assessment, reporting, and quality improvement to ensure that a product or service
(e.g., environmental data) meets defmed standards of quality with a stated level of confidence.
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Quality Assurance Project Plan (QAPP): a formal technical document containing the detailed
procedures for assuring the quality of environmental data prepared for each EPA environmental
data collection activity and approved prior to collecting the data.
quality control (QC): the overall system of technical activities whose purpose is to measure and control
the quality of a product or service so that it meets the needs of users. The aim is to provide
quality that is satisfactory, adequate, dependable, and economical.
Quality Management Plan (QMP): a formal document describing the management policies, objectives,
principles, organizational authority, responsibilities, accountability, and implementation protocols
of an agency, organization, or laboratory for ensuring quality in its products and utility to its
users. In EPA, QMPs are submitted to QAMS for approval.
range: the numerical difference between the minimum and maximum of a set of values.
‘sample: a single item or specimen from a larger whole or group, such as any single sample of any
medium (air, water, soil, etc.).
2 sample: a group of samples from a statistical population whose properties are studied to gain information
about the whole.
sample variance: a measure of the dispersion of a set of values.
sampling: the process of obtaining a subset of measurements from a population.
sampling error: the error due to observing only a limited number of the total possible values that make
up the population being studied. It should be distinguished from errors due to imperfect selection,
bias in response, and errors of observation, measurement, or recording, etc.
scoping team: the group of people that will carry out the DQO Process. Members include the decision
maker (senior manager), representatives of other data users, senior program and technical staff,
senior managers (decision makers), someone with statistical expertise, and a QAJQC advisor (such
as a QA Manager).
standard deviation: the square root of the variance.
statistic: a function of the sample measurements; e.g., the sample mean or standard deviation.
study design: a study design specifies the final configuration of the environmental monitoring effort to
satisfy the DQOs. It includes the types of samples or monitoring information to be collected;
where, when, and under what conditions they should be collected; what variables are to be
measured; and the Quality Assurance and Quality Control (QA/QC) components that ensure
acceptable sampling error and measurement error to meet the decision error rates specified in the
DQOs. The study design is the principal part of the QAPP.
total study error: the sum of all the errors that are incurred during the process of sample design through
data reporting. Total study error is related to decision error.
113
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true: being in accord with the actual state of affairs.
Type I error: an error that can occur during a statistical hypothesis test. A Type i error occurs when
a decision maker rejects the null hypothesis (decides that the null hypothesis is false) when it is
actually true.
Type II error: an error that can occur during a statistical hypothesis test. A Type IT error occurs when
the decision maker accepts the null hypothesis (decides that the null hypothesis is true) when it
is actually false.
uncertainty: a measure of the total variability associated with sampling and measurement that includes
the two major error components: systematic error (bias) and random error (imprecision)
114
-------
APPENDIX IV
B LBLIOGRAPHY
General
Environmental Protection Agency (EPA). 1987. Data Quality Objectives for Remedial Response
Activities: Development Process. EPA/540/G-87/003.
Environmental Protection Agency (EPA). 1987. Data Quality Objectives for Remedial Response
Activities, Example Scenario: RIIFS Activities a: a Site with Contaminated Soil and Ground
Water. Office of Emergency and Remedial Response. EPA/540/O-87/004.
Environmental Protection Agency (EPA). 1991. Rote of the Baseline Risk Assessment in Superfund
Remedy Selecting Decision. Office of Solid Waste and Emergency Response. OSWER
Directive 9355.0-30.
Environmental Protection Agency (EPA). 1992. Guidance for Data Useability in Risk Assessment:
Final. Office of Emergency and Remedial Response. Part A: 9285.7-09A.
Environmental Protection Agency (EPA). 1992. Guidance on Implementation of the Superfund
Accelerated Cleanup Model under CERCJA and the NCP. OSWER Directive No. 9203.1-03.
Environmental Protection Agency (EPA). 1992. Interim Draft EPA Requirements for Quality
Management Plans. EPA/QA/R-2.
Environmental Protection Agency (EPA). 1992. Piloting the New Superfund Accelerated Cleanup
Model ‘The New Superfund Paradigm.” Office of Solid Waste arid Emergency Response.
Environmental Protection Agency (EPA). 1992. Review of Draft Superfund Quality
AssuranceJQualiry Control (QAJQC) Fact Sheet. Office of Solid Waste and Emergency
Response.
Environmental Protection Agency (EPA). 1992. SACM Program Management Update: Assessing
sites Under the Supetfund Accelerated Cleanup ModeL Office of Solid Waste and Emergency
Response. 9203.1-051.
Environmental Protection Agency (EPA). 1992. SACM Program Management Update: Early Action
and Long-Term Action Under the Superfund Accelerated Cleanup Mode!. Office of Solid
Waste and Emergency Response. 9203.1-051.
Environmental Protection Agency (EPA). 1992. SACM Program Management Update: Enforcement
Under the Supeifund Accelerated Cleanup Model. Office of Solid Waste and Emergency
Response. 9203.1-051.
115
-------
Environmental Protection Agency (EPA). 1992. SACM Pm gram Management Update: Identifying
SACM Program Management Issues. Office of Solid Waste and Emergency Response.
9203.1•05 1.
Environmental Protection Agency (EPA). 1992. SACM Program Management Update: Regional
Decision Teams. Office of Solid Waste and Emergency Response. 9203.1-051.
Environmental Protection Agency (EPA). 1992. Supe,fund Accelerated Cleanup Model. Office of
Solid Waste and Emergency Response. Publication number 9203.1-01.
Environmental Protection Agency (EPA). 1993. EPA Quality System Requirements for Environmental
Programs (Draft). EPAIQ A/R- 1.
Environmental Protection Agency (EPA) 1993. EPA Requirements for Quality Assurance Project
P!ai s for Environmental Data Operations (Draft Final). EPA/QA/R-5.
Environmental Protection Agency (EPA), 1993. Guidance for Planning for Data Collection i t t
Support of Environmental Decision Making Using the Data Quality Objectives Process.
EPA/QA/G-4.
Environmental Protection Agency (EPA) 1993. Guidance for Conducting Environmental Data
Quality Assessments. EPA/QAIG-9
Zirschky and Gilbert, July 9, 1989 Deiecting hot spots at hazardous waste sites.” Chemical
Engineering, pp. 97-100.
State the Problem
Environmental Protection Agency (FPA January 1987. Technology Briefs, Data Requirements for
Selecting Remedial Action Te hr’.ology Hazardous Waste Engineering Research Laboratory.
EPA/600/2-87/001.
Environmental Protection Agency (EPA) August 1988. CERCLA Compliance with Other Laws
Manual. Office of Emergency and Remedial Response. EPA/540/G-89/006.
Environmental Protection Agency (EPA). October 1988. Guidance for Conducting Remedial
investigations and Feasibility Stuthes Under CERCL4. Office of Emergency and Remedial
Response. EPA/540/G-891004.
Environmental Protection Agency (EPA). Match 1989. Soil Sampling Quality Assurance User’s
Guide (Second Edition). Environmental Monitoring Systems Laboratory. EPA/60018-891046.
Environmental Protection Agency (EPA). July 1989. Risk Assessment Guidance for Superfund,
Human Health Evaluation Manual: Part A. Office of Solid Waste and Emergency Response.
9285.701 A.
116
-------
Environmental Protection Agency (EPA). August 1990. Guidance on Expediting Remedial Design
and Remedial Action. Office of Emergency and Remedial Response. EPA/5401G-90/006.
Environmental Protection Agency (EPA). October 1990. Guidance for Data Useability in Risk
Assessment. Office of Emergency and Remedial Response. EPA/540/G-90/008.
Environmental Protection Agency (EPA). October 1990. Subsurface Contamination Reference Guide.
Office of Emergency and Remedial Response. EPA/540/2-90/0l 1.
Environmental Protection Agency (EPA). December 1991. Risk Assessment Guidance for Superfluid:
Volume 1.. Human Health Evaluation Manual: Parr C. (Risk Evaluation of Remedial
Alternatives). Office of Research and Development. EPAJ54OIE . -921004.
Environmental Protection Agency (EPA). December 1991. Risk Assessment Guidance for Superfwzd:
Volwne I- Human Health Evaluation Manual: Part B. (Development of Risk-based
Preliminary Remediation Goals). Office of Research and Development. EPAJ54OIR-921003.
Environmental Protection Agency (EPA). December 1991. Risk Assessment Guidance for Superfund:
Volume 11 Environmental Evaluation Manual. Office of Emergency and Remedial Response.
EPA 54W1-89 001.
Environmental Protection Agency (EPA). September 1991. GuIdance for Performing Preliminary
Assessments Under CERCLA. Office of Emergency and Remedial Response. EPA154O/G-
91/013.
Environmental Protection Agency (EPA), September 1992. Guidance for Performing Site Inspections
Under CERCL4. Office of Emergency and Remedial Response. EPA/5401R-921021.
Environmental Protection Agency (EPA). Handbook Ground Water. Robert S. Kerr Environmental
Research Laboratory. EPA1625/6-87/0 16.
Identify the Decision
Environmental Protection Agency (EPA). October 1988. Guidance for Conducting Remedial
Investigations and Feasibility Studies Under CERCLA. Office of Emergency and Remedial
Response. EPAI54O/G-89/004.
Environmental Protection Agency (EPA). August 1990. Guidance on Expediting Remedial Design
and Remedial Action. Office of Emergency and Remedial Response. EPAJ54OIG-90/006.
Environmental Protection Agency (EPA). September 1991. Guidance for Performing Preliminary
Assessments Under CERCL4. Office of Emergency and Remedial Response. EPAJ54G/G-
91/013.
Environmental Protection Agency (EPA). September 1992. Guidance/or Performing Site Inspections
Under CERCLA. Office of Emergency and Remedial Response. EPA/5401R-92/02 1.
117
-------
Environmental Protection Agency (EPA). 1992. SACM Program Management Update: Assessing
Sites Under the Superfund Accelerated Cleanup Model. Office of Solid Waste and Emergency
Response. 9203.1-051.
Environmental Protection Agency (EPA). 1992. SACM Program Management Update: Early Action
and Long-Term Action Under the Supe,fwzd Accelerated Cleanup Model. Office of Solid
Waste and Emergency Response. 9203.1-051.
Environmental Protection Agency (EPA). 1992. SACM Program Management Update: Enforcement
Under the Superfund Accelerated Cleanup Model. Office of Solid Waste and Emergency
Response. 9203,1-051.
Environmental Protection Agency (EPA). 1992. SACM Program Management Update: Identifying
SACM Program Management Issues. Office of Solid Waste and Emergency Response.
9203.1-051.
Environmental Protection Agency (EPA). 1992. SACM Program Management Update: Regional
Decision Teams. Office of Solid Waste and Emergency Response. 9203.1-051.
Identify the Inputs
Environmental Protection Agency (EPA). August 1988. CERCLA Compliance with Other Laws
Manual. Office of Emergency and Remedial Response. EPAJ54OIG-89/006.
Environmental Protection Agency (EPA). October 1991. Guidance for Data Useabilily in Site
Assessment (Draft). Office of Emergency and Remedial Response.
Environmental Protection Agency (EPA). December 1991. Risk Assessment Guidance for Superfund:
Volume 1- Human Health Evaluation Manual: Part B. (Development of Risk-based
Preliminary Remediation Goals) Office of Research and Development. EPA/5401R-92/003.
Environmental Protection Agency (EPA). April 1992. Guidance for Data Useability in Risk
Assessment: Part A. Office of Emergency and Remedial Response. Publication 9285.7-09A.
Define the Study Boundaries
California Department of Health Services. 1986. The Cal jfornia State Mitigation Decision Tree
Manual. Sacramento, CA.
California Department of Transportation. 1988. Standard Speciflcatioivs. Sacramento, CA.
Cross, F.L. Jr., Cameron, W.W. Jr. 1974. Handbook of Swimming Pool Construction, Maintenance
and Sanitation. Technomic, Westport, CT.
118
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Environmental Protection Agency (EPA) 1988. Ground Water Modeling: An Overview and Status
Report. EPA/60012-89/028.
Environmental Protection Agency (EPA) 1989. Determining Soil Response Action Levels Based on
Potential Contaminant Migration to Ground Water: A Compendium of Examples. EPAI54O/2-
89/057.
Environmental Protection Agency (EPA). t989. Guidance on Applying the Data Quality Objectives
Process for Ambient Air Monitoring Around Superfund Sites (Stages 1 and 2). Office of Air
Quality and Planning and Standards. EPA/450/4-89/015.
Environmental Protection Agency (EPA). 1989. Soil Sampling Quality Assurance User’s Guide.
Environmental Monitoring Systems Laboratory. Las Vegas, NV. EPAJ600/8-891046.
Environmental Protection Agency (EPA). 1991. Representative Sampling Guidance, Vol 1, SoiL
OSWER Directive 9360.4-10.
Gibbons, RD. March-April 1990. “A General Statistical Procedure for Ground-Water Detection
Monitoring at Waste Disposal Facilities.” Ground Water 28:2:235-43.
Hydak, P.F. and 1-LA. Loaciga. March 1992. “A Location Modeling Approach for Groundwater
Monitoring Networking Augmentation.” Water Resources Research 28:3:643-649.
International Association of Plumbing and Mechanical Officials. 1985. Unjfonn Plumbing Code. Los
Angeles, CA.
International Conference of Building Officials. 1985. Un form Building Code. Whittier, CA.
Kimbrough, R.D., H. Falk, P. Stehr and G. Fries. 1984. “Health implications of 2,3,7,8-
tetra;chlorodibenzodioxin (TCDD) contamination of residential soil.” I. Toxicology, Environ.
Health, 14:47.
Koeford, K., R. Fisher, and R. Johnson. December 12, 1988. Personal Communications.
Krebs, R.D. and R.D. Wallace. 1971. Highway Materials. McGraw Hill. New York.
McBear, E.A. and F. A. Rovers. 1992. “Estimation of the probability of Exceedance of Contarrunant
Concentrations.” Ground Water: Monitoring Review. Winter 1992: 115-19.
Monahan, E.J. 1986. Construction of and on Compacted FilLs. .1. Wiley and Sons, New York.
National Fire Protection Association. 1984. National Electrical Code. Quincy, Massachusetts.
Nichols, H.L. 1974. Moving the Earth, Workbook of Excavation. 3rd ed. North Castle Books,
Greenwich, CT.
119
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Peck, R.B., WE. Hansen and T.H. Thornburn. 1979. Foundation Engineering. 2nd ed. J. Wiley and
Sons, New York.
Reynolds, S.D., P.W. Hadicyand and R.M. Sedman. 1990. “A health based approach for evaluating
soils at hazardous waste sites using the AAL soil contact criterion.” Risk Analysis 10:57 1.
Sedman, R.M. 1990. “The development of applied action levels for soil contact: A scenario for the
exposure of humans to soil in a residential setting.” Environ. Health Perspecl. 84-203.
Sowers, G.F. 1979. Introductory Soil Mechanics and Foundations: Geozechnical Engineering. 4th
ed. MacMillan, New York.
Spruill, T.B. and L. Candale. 1990. “Two Approaches to Design of Monitoring Networks.” Ground
Water GRWAAP May/June 1990 28.3:430-42.
Specify Limits on Decision Errors
Environmental Protection Agency (EPA). 1989. Methods for Evaluating the Attainment of Cleanup
Standards: Volume 1: SoiLc and Solid Media. EPA/230/02-891042. Office of Policy, Planning,
and Evaluation.
Environmental Protection Agency (EPA). 1989. Methods for Evaluating the Attainment of Cleanup
Standards: Vo(wne 2: Ground Water. EPAI23OIR-92/014. Office of Policy. Planning, and
Evaluation.
Gilbert, Richard 0. 1987. Statistical Methods for Environmental Pollution Monitoring. New York:
Van Nostrand Reinhold Company.
Natrella, Mary Gibbons. 1963. Experimental Statistics. US Department of Commerce, National
Bureau of Standards Handbook 91.
Snedecor, G.W. and W.G. Cochran. 1980. Statistical Methods, 7th Edition. Ames, Iowa: Iowa State
University Press.
Steel, R.G.D., and J. H. Torrie. 1980. Principles and Procedures of Statistics. New York: McGraw-
Hill Book Company.
Optimize the Design
Barnett, V. and T. Lewis. 1984. Outliers in Statistical Data. New York: John Wiley & Sons.
Cochran W. 1977. Sampling Techniques. New York: John Wiley & Sons.
120
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Environmental Protection Agency (EPA). December 29, 1980. Interim Guidelines and Specifications
for Preparing Quality Assurance Project Plans. QAMS-005/80. Office of Monitonng
Systems and Quality Assurance, Office of Research and Development.
Environmental Protection Agency (EPA). 1986. Test Methods for Evaluating Solid Waste (SW-846):
Physical/Chemical Methods, Third Edition. Office of Solid Waste.
Environmental Protection Agency (EPA). 1989. Removal Program’s Representative Sampling
Guidance Document. OSWER Directive: 9360.4-10.
Environmental Protection Agency (EPA). 1993. Guidance Document on the Statistical Analysis of
Ground-Water Monitoring Data at RCRA Facilities , Office of Solid Waste.
Environmental Protection Agency (EPA). 1989. Methods for Evaluating the Attainment of Cleanup
Standards: Volume I: Soils and Solid Media. EPA 230/02-89-042. Office of Policy,
Planning, and Evaluation.
Environmental Protection Agency (EPA) 1993 Methods for Evaluating the Attainment of Cleanup
Standards: Volume 2: Ground Water EPAJ23O/R-921014. Office of Policy, Planning, and
Evaluation.
Environmental Protection Agency (EPA) 1990 A Rationale for the Assessment of Errors in the
Sampling of Soils. Office of Research and Development. EPA1600/4-90/013.
Environmental Protection Agency (EPA) Apnl. 1992. Guidance for Data Useability in Risk
Assessment (Pan A). Publication 985 7-09 A. Office of Emergency and Remedial Response.
Gilbert, Richard 0. 1987. Statistical Mrthaij for Environmental Pollution Monitoring. New York:
Van Nostrand Reinhold Compan
tusGovERIa.IEMrPRINTI N GOFRc E 1994 — 300 -s74 lOk000
121
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Section 3
-------
FIELD SCREENING
STUDENT PERFORMANCE OBJECTIVES
At the conclusion of this unit, students will be able to:
1. List and give a functional description of the classes of
chemicals on the Target Compound List.
2. Determine the uses and limitations of the x-ray fluorescence
techniques.
3. Determine the uses and limitations of soil gas techniques.
4. Describe the theory and use of the enzyme immunoassay
test.
5. Determine the uses and limitations of magnetics,
electromagnetics, and ground-penetrating radar.
6. List and describe other types of inexpensive field test kits.
NOTE : Students may use all references and material provided
in the course, unless otherwise specified, to perform
the objectives. Students are expected to perform each
objective without error.
1/96
-------
FIELD
SCREENING
WHY FIELD SCREENING
• Ltmits resources necessary
• Limits time
• Reduces large areas requiring further
investigation
TARGET COMPOUND LIST
• List of 148 chemicals
• Toxic and prevalent
• Updated periodically
1/96 1 Field Screening
-------
TARGET COMPOUND LIST ( cont. )
• Volatiles
• SemivolatUes (BNA)
• Pesticides/PCBs
• Metals
• Cyanide
Field Screening 2 11%
-------
TARGET COMPOUND LIST
Volatile Compounds°
Acetone 1 ,2-Dichloropropane
Benzene cLc- 1 ,3-Dichloropropenc
Brotnodich loromethane trans-i ,3-Dichtoropropene
Bromoform Ethylbenzene
Brornomethane 2-Hexanone
2-Butanone Methylene chloride
Carbon disulfide 4-Methyl-2-pentanone
Carbon tetrachloride Styrene
Chlorobenzene 1,1,2 ,2-Tetrachloroethane
Chioroethane Tetrach loroethene
Chloroform Toluene
Ch loromethane 1,1, 1-Trich loroethane
Dibromoch loromethane 1,1 ,2-Trichloroethane
1, i-Dichloroethene Trichioroethene
1,2-Dichioroethene (total) Vinyl acetate
1,1-Dichioroethane Xylenes (total)
1 ,2-Dichloroethane
BTEX
Benzene
Toluene
Ethylbenzene
Xylenes (total)
BTEX compounds are included in an analysis of volatile compounds, or they can be
analyzed as a separate group.
7 /96 3 Field Screening
-------
TARGET COMPOUND LIST (continued)
Semivolatile Compounds
Base-Neutral Extractables
bis(2-Chtoroethyl)ether Anthracene
1 ,3-Dichlorobenzerie Di-n-butylphtalate
1 ,4-Diclilorobenzene Fluoranthene
1 ,2-Dichlorobenzene Pyrene
bis(2-Chloroisopropyl)ether 3,3 ‘-Dichlorobenzidine
N-Nitroso-di-n-propylamine Benz(a)anthracene
Hexachioroethane Chrysene
Nitrobenzene bis(2-Ethylhexyl)phthalate
Isophorone Di-n-octylphthalate
bis(2-Chloroethoxy)methane Benzo (b)fluoranthene
1,2 ,4-Trichlorobeazene Benzo(k)fluoranthene
Naphthalene Benzo(a)pyrene
Hexachiorobutadiene Indeno(1 ,2 ,3-cd)pyrene
2-Chloronaphthalene Dibenz(a,h)anthracene
Dimethylphthalate Benzo(g ,h ,i)perylene
Acenaphthylene Hexachiorocyclopentadiene
2 ,6-Dinitrotoluene N-Nitrosodipheny lamine
Acenaphthene Butylbenzyl phthalate
2 ,4-Dinitrotoluene 4-Chioroaniline
Diethylphthalate 2-Methylnaphthalene
4-Chiorophenyl-phenyl ether 2-Nitroaniline
Fluorene 3-Nitroaniline
4-Bromophenyl-phenyl ether Dibenzofuran
Hexachlorobenzene 4-Nitroaniline
Phenanthrene
Acid Extractables
Phenol 4-Nitrophenol
2-Chlorophenol 4, 6-Dinitro-2-methy]phenol
2-Nitrophenol Pentachiorophenol
2,4-Dimethyiphenol Benzyl alcohol
2,4-Dichiorophenol 2-Methylpheriol
4-Ch loro-3-methylphenol 4-Methyiphenol
2,4, 6-Trichlorophenol Benzoic acid
2 ,4-Dinitropheno! 2 ,4,5-Trichlorophenol
Field Screening 4 1/96
-------
TARGET COMPOUND LIST (continued)
Pesticides and PCBs
Aidrin Endrin
alpha-BHC Endrin ketone
beta-BHC Heptachior
gamma-BHC (Lindane) Heptachior epoxide
delta-BHC Methoxychior
aipha-Chiordane Aroclor- 1016
gamma-Chlordane Aroclor-1221
4,4,-DDT Aroclor-1232
4,4-DDE Aroc lor-1242
4,4-DDD Aroclor-1248
Die ldrin Aroclor-1254
Endosulfan Aroclor-1260
Endosulfan II Toxaphene
Endosulfan sulfate
Inorganic Target Analyte List (TAL)
Metals
Aluminum Magnesium
Antimony Manganese
Arsenic Mercury
Barium Nickel
Beryllium Potassium
Cadmium Selenium
Calcium Silver
Chromium Sodium
Cobalt Thallium
Copper Vanadium
Iron Zinc
Lead Cyanide
Reference: U.S. EPA Contract Laboratory Program Statement of Work for Organic and
Inorganic Analysis (refer to the most current publication).
11% 5 Field Screening
-------
FIELD SCREENING METHODS
• X-ray fluorescence (XRF)
• Soil gas
• Enzyme immunoassay (EIA)
• Geophysics
• Inorganic test kits
X-RAY
FLUORESCENCE
X-RAY FLUORESCENCE
• Field portable instrument with
radioactive source
• Quantitative metals analysis
Field Screening 6 11%
-------
X-RAY FLUORESCENCE (cont. )
• Source irradiates sample
• Electrons excited and fluoresce
• Wavelength indicative of element
• Intensity indicates concentration
XRF USES
• Battery and wire burning sites
• Abandoned mines
• Lead in soil
• Lead in paint
XRF LIMITATIONS
• Penetration in centimeters
• Need site-specific calibration
• Wet soil major matrix interference
1/96 7 Field Screening
-------
SOIL GAS
Reid Screening 8 11%
-------
CROSS SECTION
Source P Vapors
Vadose
I
Leachate
H Regional Flow
PLAN VIEW
Plume
Regional Flow
Saturated
1/96
Field Screening
9
-------
SOIL GAS USES
• Delineate groundwater plumes
• Locate monitoring wells
• Locate soil contamination
SO1L GAS LIMITATIONS
• Pnmanly vo’atile organic compound
identification
• Limited use in clay
• Semiquantitative analysis
ENZYME
IMMUNOASSAY
(EtA)
Field Screening 10 1/96
-------
THEORY OF OPERATION
• ImmunoasSay tests work by detecting
the binding of chemical-specific
antibodies and antigens
• Detection is accomplished by
coupling an antibody or an analyte
with a tag that can be detected
1/96 II . Field Screening
-------
STEP 1: ADD
SAMPLE/CALl BRATORS
Adapted from Millipore product literature, EnviroGard Test Kits, 1993, with permission.
STEP 2: ADD ENZYME CONJUGATE
ii., 0
//j /
fl Antibody
0 Analyte in sample Enzyme conjugate
Adapted from Millipore product literature, EnviroGard Test Kits, 1993, with permission.
0
0
0
0
Antibody
0 Analyte in sample
Field Screening
12
1/96
-------
STEPS 3 AND 4:
INCUBATE AND WASH
• Enzyme conjugate
Adapted from Millipore product literature, EnviroGard tm ’ Test Kits, 1993, with permission.
STEPS 5 AND 6: ADD SUBSTRATE
AND CHROMOGEN
Antibody
• Enzyme conjugate
r.i Chromogen Substrate
Adapted from Millipore product literature, EnviroGard Test Kits, 1993, with permission.
if Antibody C) Analyte in sample
I
0 Analyte in sample
1/96
13
Field Screening
-------
STEP 7: THE CHROMOGEN
IS CONVERTED
Substrate
Adapted from Millipore product literature, EnviroGard Test Kits, 1993, with permission.
STEPS 8 AND 9: STOP REACTION
AND READ RESULTS
1 Antibody
C) Analyte in sample Enz m. conFi at.
Chromogen
II Antibody
Adapted from Millipore product literature, EnviroGard Test Kits, 1993, with permission.
U [ ] Product
Field Screening
14
1/96
-------
EIA USES
Pesticides and Herbicides
• DOT
• Atrazine
• Chiordane
• 2, 4,-D
EIA USES (cont.)
Fuels and Heavy Hydrocarbons
• Benzene
• BTEX
• Polycyclic aromatic
hydrocarbons (PAHs)
• TPH
EIA USES (cont.)
Miscellaneous Compounds
• TNT/RDX
• Polychionnated bipheriyis (PCBs)
• Pentachiorophenol (PCP)
• Mercury
1/96
15
Field Screening
-------
EIA LIMITATIONS
• Sensitivity
• Refrigeration
• Limited shelf life
• Cross-reactivity
• Draft SW-846 methods
S-27
GEOPHYSICS
S-28
GEOPHYSICS
• Magnetics
• Electromagnetics (EM)
• Ground-penetrating radar (GPR)
S-29
Field Screening 16 1/96
-------
MAGNETICS
—
• Earths magnetic field Intensity measured
• Total field or vertical component
• Ferromagnetic material detected
• Passive method
MAGNETICS USES
• Drum location
• Landfill boundaries
• Screening for drill sites
MAGNETICS LIMITATIONS
• Only detects iron and steef
• Depth determination difficult
• Interferences/false positives
1196 17 Field Screening
-------
ELECTROMAGNETICS (EM )
• Electric field induces secondary tields
• Secondary fields related to
conductivity
• Conductivity read directly
• Active method
EM USES
• Drum location
• Conductive plumes
• Landfill boundaries
• Utilities, pipelines, etc.
EM LIMITATIONS
• Limited depth of penetration
• Operators need to be trained
• Interpretations by geophysicist
Fieki Screening 18 1/96
-------
GROUND-PENETRATING
RADAR (GPR)
• Electromagnetic energy
transmitted and received
• Reflections at matenal horizons
• Metal or changes in geology
detected
• Active method
GPR USES
• Drum and underground storage
tank locations
• Trench/landfill boundaries
• Geologic horizons
• Water table location
GPR LIMITATIONS
• Poor penetration in clay
• Difficult to interpret
• Expensive equipment
1/96 19 Field Screening
-------
ADDITIONAL SCREENING
METHODS
ADDITIONAL SCREENING METHODS
• Chlorine detection
• Inorganic kits
• Field instrumentation
CHLORINE KITS - DEXSIL®
• Detects chionne in compound
• Used for PCBs in oil or soil
FLeld Screening 20 1/96
-------
INORGANIC TEST KITS
• Uses color change for detection
• Interpretation by color wheel or
spectrophotometer
• Cyanide, copper, lead 1 nickel, others
FIELD SCREENING INSTRUMENTS
• Snapshot P D
• ICE monitor
• Others
1/96
21
Field Screening
-------
REFERENCES
U.S EPA. 1989. Methods for Evaluating the Attainment of Cleanup Standards: Volume 1—Soils
arid Solid Media. EPA 230/02-89-042. U.S. Environmental Protection Agency, Washington, DC,
U S. EPA. 1991. Removal Program, Representative Sampling Guidance: Volume 1—Soil. Interim
Final OSWER Directive 9360.4-10. U.S. Environmental Protection Agency, Washington, DC.
U S EPA 1992. Guidance for Data Useabihty in Risk Assessment (Part A). Final Report.
Publication 9285 7-09l A Office of Emergency and Remedial Response, Washington, DC.
1196 23 Field Screening
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Section 4
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DOCUMENTATION
STUDENT PERFORMANCE OBJECTIVES
At the conclusion of this unit, students will be able to:
1. List different types of field documentation.
2. Identify the components of each type of documentation.
3. Prepare documentation forms in accordance with applicable
field standard operating procedures, given the proper forms
of documentation.
4. Describe the elements of training required by the U.S.
Department of Transportation (DOT).
NOTE : Students may use all references and material provided
in the course, unless otherwise specified, to perform
the objectives. Students are expected to perform each
objective without error.
1/96
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DOCUMENTATION
SAMPLE DOCUMENTATION
• Field logbooks
• Sample labels
• Site maps
SAMPLE DOCUMENTATION (cont. )
• Photographs
• Chain of custody
• Other documentation
1/96 1 Documentation
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SAMPLE DOCUMENTATION (cont. )
Field logbooks - provide daily records
of significant events, observations, and
measurements dunng field investigations
FIELD DOCUMENTATION
Best Practices
• Use a bound notebook
• Record all original data in
nonerasable waterproof ink
• Correct errors by crossing a
single line through the error and
initialing and dating the correction
FIELD DOCUMENTATION (cont.)
Best Practices
• Field records should be direct and
succinct
• Documenter should sign and date
each page
Documentation 2 1/96
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FIELD LOGBOOK ENTRIES
• Date and time of entry
• Purpose of sampling
• Name and address of field contacts
(federal, state, and local representatives)
FIELD LOGBOOK ENTRIES (cont. )
• Description of sample
• Description of sampling point
• Date and time of sample collection
FIELD LOGBOOK ENTRIES (cont. )
• Sample identification number
• Field observations
• Field measurements
(e.g , pH, flammability)
1/96 3 Documentation
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SAMPLE IDENTIFICATION
All sample containers should be labeled
with the following eight categones of
identifying information
1 Project code
2 CLP case and sample
number
SAMPLE IDENTIFICATION (cant. )
3 Station location and
number
4 Date and time of
sample location
5 Preservative
SAMPLE IDENTIFICATION (cant. )
6 Requested analysis
7 Signature
8. Remarks
Documentation 4 1/96
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PHOTO DOCUMENTATION
__________________ Date __________________
Time
Roll # ________________
Frame # ______________
Photographer’s Name —
Location _______________
Descnpt ion ____________
Viewing Direction _______
Signature of Photographer
SAMPLE LOCATION MAP
(not to scale)
VALLEVEROOK AVENUE
PAVED
DRIVE
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SAMPLE CHAIN OF CUSTODY
A reconstruction of who had access
to the sample from the time it was
collected until produced in court
1/96
5
Documentation
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NEIC SAMPLE CUSTODY
A sample is undei custody if
• It is in your possession
• It is in your view after being in your
possession
• It was in your possession and then you
locked it up to prevent tampering
• It is held in a designated secure area
RULES GOVERNING
TRANSPORTATION OF SAMPLES
49 CFR 171-1 79
• New regulations published
December 21, 1990
• Effective date October 1, 1991
NEW RULING
• Adopts United Nations labels and placards
• Adopts UN identification numbers for
hazardous materials
• Provides packing standards based on
performance cnteria
• Makes U S standards compatible with
international standards
Documentation 6 1/96
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SCOPE OF TRAINING
REQUIREMENTS
• Persons involved in transportation of
hazardous materials
• Categories
- General awareness/familiarization training
- Function-specific training
- Safety training
- Driver training
TRAINING REQUIREMENTS
• Initial training before October 1, 1993
(if hired before July 2, 1993)
• Train within 90 days of employment
• Refresher training once every 3 years
• DOT, private agency, or employer can provide
training (must have Section 172 704 criteria)
HAZARDOUS MATERIALS
A substance or material in a quantity
or form capable of posing an
unreasonable risk to health, safety,
and property when transported in
commerce
1/96 7 Documentation
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PROJECT NO x iii x (PRoJEcT LEADER
REMARKS
PROJECT NAME/LOCATION SFHM OUI
SAMPLE TYPES
SAMPLERS (SIGN)
ANALYSES I
/ : //EuARKs
STATION NO DATE TIME 8
STATION LOCATION ESCRIPTION
RELINQUISHED BY DATE/TIME
tP .4’
RECEIVED BY
(pftp )
RELINOUISH b BY
(P lT)
DATE/TIME
RECEIVED BY
54G
RELINQUISHED BY DATE/TIME
RECEIVED v
cP I)
RELINQUISHED BY
(PR I)
DATE/TIME
RECEIVED BY
(PIT)
00
-------
DOCUMENTATION
taken from:
EPA/540/P-87/00 1
(OSWER Directive 9355.0-14)
December 1987
A COMPENDIUM OF SUPERFUTND
FIELD OPERATIONS METHODS
(Section 4)
OFFICE OF EMERGENCY AND REMEDIAL RESPONSE
OFFICE OF WASTE PROGRAMS ENFORCEMENT
U.S. ENVIRONMENTAL PROTECTION AGENCY
WASHINGTON, DC 20460
1/96 9 Documentation
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SECTION 4
SAMPLE CONTROL, INCLUDING CHAIN OF CUSTODY
4.1 SCOPE AND PURPOSE
This section describes procedures for sample Identification and chain or custody. The purpose of
these procedures is to maintain the quality of samples during collection, transportation, and storage for
analysis Sample control and chain-of-custody procedures specific to the Contract Laboratory Program
(CLP) are presented in the User’s Guide to t!ie Contract Laboratory Program.
4.2 DEFINITIONS
Sample
Physical evidence collected for environmental measuring and monitoring. Evidence includes
remote-sensing imagery and photographs.
Site Manager (SM)
The individual responsible for the successful completion of a work assignment within budget
and schedule. The person is also referred to as the Site Project Manager or the Project
Manager and is typically a contractors employee (see Subsection 1.1).
4.3 APPLICABILITY
When environmental measurthg or monitoring data are collected for the Environmental Protection
Agency (EPA), workers should refer to the procedures In this section
4.4 RESPONSIBILITIES
The SM or designee is responsible for monitoring compliance with these procedures. In general, it is
desirable to appoint one person to be responsible for Implementing sar ple control procedures (i.e field
operations leader) However, each sampler Is responsible for the actMties described In Subsections 4.5
and 4 6.
4.5 RECORDS
The following recorth are kept
• Sample identification tags (varies with the EPA regIon, see Subsection 4.7 and Exhibit 5-7)
• Sample traffic reports (e g. Special Analytical SeMces (SAS): see Exhibits 5-2, 5-3, and 5-9)
• Chain.oI.custody (COC) forms and records (see Exhibits 5-4. 5-5, and 5-6)
• Receipt-for-samples forms (varies among EPA regions; see Subsection 4 7 and Exhibit 4-3)
1/96 ii Documentation
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• Field investigation Team (FIT) receipt (for sample forms and field notebooks not serially numbered
by the U.S. EPA)
• Field notebooks
• Airbills or bills of lading
• Dioxin analysis forms (as applicable)
• Photographic logs
Subsection 4.6 describes procedures for these records; Subsection 5.1.6 shows completed exhibits of
the first three items.
4.6 PROCEDURES
Sample identification documents must be prepared to maintain sample identification and chain of cus-
tody. The following are sample Identification documents:
• Sample iderttilicatlon tags
• Sample traffic reports
• Chain-of-custody records
• Receipt-for-samples forms
• Custody seals
• Field notebooks
These documents are usually numbered (serialized) by EPA. Some varieties of custody seals, field
notebooks, or photographic logs may not be serialized.
The following additional forms are used for samples shipped to CLP laboratories:
• Organic traffic reports
• Inorganic traffic reports
• High-hazard traffic reports
• SAS request forms
• Dioxin shipment records (as applicable)
Completed examples of these forms are in Subsection 5 1 6 of this compendium
Docuineniation 12 11%
-------
The organizations document control officer (designated on exhibits in this subsection as the Regional
Document Control Officer or RDCO) or another designated person maintains a supply of the documents
listed above, including field note books The document control officer is responsible for the inventory of
serialized documents and the assignment of these documents to specitic projects Unused field docu-
ments are usually returned to the document control officer at the end of the field sampling event The
document control officer notes the return of these documents In the serialized document logbook In some
EPA regions, unused field documents are retained by the sampler to whom they were originally assigned
for use on future projects The sampler maintains a personal logbook In which is recorded the final disposi-
tion of all relevant field Information. Unused, returned documents may be checked out to another project
by the RDCO, as needed. A cross reference of serialized field documents is usually maintained for each
proiect in the project files A sample cross-reference matrix is shown in Exhibit 4-1.
The document control officer orders sample identificatIon tags, receipt-for samples forms, custody
seals, and chain-of-custody records from the EPA regional offices. Traffic reports and SAS request forms
are obtained through the Sample Management Office (SMO) representative.
Exhibit 4-2 shows how the sample control documents can be Integrated into the document control pro-
cedures used In an EPA project. The procedures for using each document are discussed below. Subsec-
tIon 4 7 discusses regional variations: however, because procedures change and vary from region to
region, the EPA eglonai Sample Coordinating Center (RSCC) should be contacted during the planning of
field activities to obtain the most current procedures Appendix A of the User’s Guide i o the CL? contains a
directory of RSCC contacts and telephone numbers.
4.6.1 Sample Identification Tags
Sample Identification tags (see Exhibit 5-7) are distributed as needed to field workers by the SM (or
designated representative). Procedures vary among EPA regions. Generally, the EPA serial numbers are
recorded in the project files, the field notebook, and the document control officer’s serialized document
logbook. Individuals are accountable for each tag assigned to them. A tag Is considered to be in an
individual’s possession until it has been filled out, attached to a sample, and transferred to another in-
dividual along with the corresponding chain-of custody record. Sample identification tags are not to be
discarded. if tags are iost, voided, or damaged, the facts are noted In the appropriate field notebook, and
the SM Is notified.
Upon the completion of the field activities, unused sample Identification tags are returned to the docu-
ment control officer, who checks them against the list of assigned serial numbers. Tags attached to those
samples that are split with the owner, operator, agent-In-charge, or a government agency are accounted
for by recording the serialized tag numbers on the receipt-for-samples form (Exhibit 4-3). Alternatively, the
split samples are not tagged but are accounted for on a chain-of-custody form.
Samples are transferred from the sample location to a laboratory or another location for analysis
Before transfer, however, a sample Is often separated Into fractions, depending on the analysis to be per-
formed Each portion Is preserved in accordance with prescribed procedures (see User’s Guide to the CLP
and Section 6 of this compendium) and is identified with a separate sample identification tag, which should
indicate in the Remarks’ section that the sample is a split sample.
1/96 13 Docwnentation
-------
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Sample indecildicailcin Type of Traffic Trait Ic TaUk Dioxin of-Custody Samples Airbili Dale
Snilsin Ta p Number Biport Number Report NumbE eport Number Foucis Record Number Form Nurriber Number Shippud
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The following information Is recorded on the tag:
• CLP Case / SAS Number(s): The unique number(s) assigned by SMO to identify the sampling
event (entered under Remarks’ heading)
• CLP Sample Number: The unique sample identificatIon number (from the TR, DSR, or PL) used
to document that sample (entered under Remarks” heading)
• Project Code: An assigned contractor project number
• Station Number: A unique identifier assigned to a samp’ing po!nt by trio sampling team leader
and listed in the sampling plan
• Date: A six-digit number indicating the year, month, and day of coflection
• Time: A four-digit number indicating the local standard time of collection using the 24-hour clock
notation (for example, 1345 for 1 45 p.m)
• Station Location: The sampling station description as specified in the sampling plan
• Samplers: Each sampler’s name and signature
• Preservative: Whether a preservative is used and the type of preservative
• Analysis: The type of analysis requested
• Tag Number: A unique serial number, stamped on each tag
• Batch Number: The sample container cleaning batch number, recorded In the “Remarks” section
• Remarks: The sampler’s record of pertinent information, such as batch number, split samples,
and special procedures
• Laboratory Sample Number: Reserved for laboratory use
The tag used for water, soil, sediment, and biotic samples contains an appropriate place for identifying
the sample as a grab or a composite, the type of sample collected, and the preservative used, if any. The
tag used for air samples requires the sampler to designate the sequence number and identify the sample
type Sample Identification tags are attached to, or folded around each sample, and are taped In place
After collection, separation, identification and preservation, a traffic report is completed and the sample
Is handled using chain-of-custody procedures discussed in the following sections If the sample Is to be
split, aliquots are piaced into similar sample containers Depending on the EPA region, sample identifica-
tion tags are completed and attached to each split and marked with the tag numbers of the other portions
and w h the word “split.” Blank or duplicate samples are labeled in the same manner as “normal” samples.
information on blanks or duplicate samples Is recorded in the field notebook Some EPA regions require
that laboratories be informed of the number of blanks and duplicates that are shipped, but not the Identity
of the quality assurance samples
The printed and numbered adhesive sample labels affixed to the traffic reports are secured to sample
containers by the sampler Forms are filled out with waterproof Ink, if weather permits. if a pen will not
function because of inclement conditions, an indelible pencil may be used If a pencil is used. a note ex-
Docu,nentaiion 16 1/96
-------
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United States
Environmental Protection Agency
Region 10
RECEIPT FOR SAMPLES
Environmental S.rvicu Division
U S Environmental Protection Agency Region 10
1200 Sixth Avanu., Ss.tti. Washington 98101
PROJECT NO PROJECT NAME
Name of Fjciliiy
SAMPLER(S) (SsgnewieJ
Facility Location
Qlit Samples Otlpred
Accepted ( I Declined
Si.tfo.,
Numb.,
On.
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Trdr lste t ,Ldby(Slg,i a ,u,eJ — Received by ISsgnjtji, ) Telephone Number
Da n. Time Title Date Time
I
Ditiribution Original to Coo iJndIor Field F les Copy to Faciiuty
N2 131
-------
plaining the conditions must be included in the field notebook. When necessary, the label is protected
from water and solvents with clear tape.
The original is sent to the SMO. The first copy is retained for the project I de The second and third
copies are sent with the shipment to the laboratory Complete instructions for the use of traffic reports are
given in the User r Guide to the CLP.
4.6.2 Sample Traffic Report (TR)
The sample documentatIon system for the CLP sample preparation program is based on the use of the
sample traffic report (TA), a four-part carbonless form printed with a unique sample ident f:ca1ion number.
One TA and its printed identification number Is assigned by the sampler to each sample collected, The
three types of TRs currently In use include organic, inorganic dioxin, and high-concentration TRs (See
Subsection 5.1 6 for examples of completed TAs)
To provide a permanent record for each sample collected, the sampler completes the appropriate TA,
recording the case number, site name or code and location, analysis laboratory. sampling office, dates of
sample collection and shipment, and sample concentration and matrix. Numbers of sample containers
and volumes are entered by the sampler, beside the analytical parameter(s) requested for particular
sample portions.
4.6.3 Chain-of-Custody Forms and Records
Because samples collected during an Investigation could be used as evidence in litigation, possession
of the samples must be traceable from the time each is collected until it is introduced as evidence in legal
proceedings. To document sample possession, chain-of-custody procedures are followed.
4.6.3.1 DefinItion of Custody
A sample Is under custody if one or more of the following criteria are met:
• The sample is in the sampler’s possession.
• It is in the sampler’s view after being in possession.
• It was in the sampler’s possession and then was locked up to prevent tamperIng.
• It is in a designated secure area
4.6.3.2 Field Custody Procedures
Only enough of the sample should be collected to provide a good representation of the medium being
sampled To the extent possible, the quantity and types of samples and the sample locations are deter-
mined before the actual fieldwork As few people as possible should handle the samples
Field samplers are personally responsible for the care and custody of the samples collected by their
teams until the samples are transferred or dispatched properly A person is usually designated to receive
Do t inenraizon 18 11%
-------
the samples from the field samplers after decontamination, this person maintains custody until the samples
are dispatched.
The SM determines whether proper custody procedures were followed during the fieldwork and
decides if additional samples are required
4.6.3.3 Transfer of Custody and Shipment
Samples are accompanied by a chain-of.custody (COC) form or record (Exhibits 5-4 and 5-5) When
transferring samples, the indMduals relinquishing and receMng them should sign, date and note the time
on the form This form documents sample custody transfer from the sampler, often through another per-
son, to the analyst, who is in a mobile or contract laboratory
Samples are packaged properly for shipment and dispatched to the appropriate laboratory for
analysis, with a separate COC record accompanying each shipment. Shipping containers are padlocked
or sealed with custody seals for shipment to the laboratory. The method of shipment, courier name(s), and
other pertinent information such as the laboratory name should be entered In the Remarks’ section of the
COC record
When samples are split with an owner, operator, or government agency, the event is noted in the
‘Remarks” section of the COC record The note indicates with whom the samples are being split The per-
son relinquishing the samples to the faciiRy or agency requests the signature of the receiving party on a
receipt.for-samples form (Exhibit 4-3) (described In the following subsection), thereby acknowledging
receipt of the samples if a representative is unavailable or refuses to sign, this situation is noted in the
Remarks section of the COC record. When appropriate, for example, when an owner’s representative is
unavailable, the COG record and receipt-for-samples form should contain a statement that the sampies
were delivered to the designated location at the designated time. A witness to the attempted delivery
should be obtained The.samples shall be secured if no one is present to receive them.
All shipments are accompanied by a COC record identifying their contents. The original form accom-
panies the shipment, the copies are retained by the sampler and returned to the sampling coordinator
if rionhazardous samples are sent by mail, the package Is registered, and a return receipt is requested
Note. Hazardous materials shall not be sent by mail If samples are sent by common carrier, a bill of
lading Is used. Air freight shipments are sent prepald. Freight bills, postal service receipts, and biils of
lading should be retained as part of the permanent documentation for the COC records
4.6.3.4 Laboratory Custody Procedures
Laboratory personnel are responsible for the care and custody of samples from the time they are
received until the samples are exhausted or returned to the laboratory sample custodian for ultimate dis-
posal Laboratory-specific variations exist, however, a generally accepted laboratory chain-of-custody pro-
cedure Is presented below Any laboratory used for the analysis of samples taken in the course of EPA
remedial response must have an adequate chain-of-custody procedure This procedure is required as an
exhibit in the Quality Assurance Project Plan (QAPjP) if the laboratory is not in the CLP
A designated custodian of laboratory samples accepts custody of the shipped samples and verifies
that the information on the sample identification tags matches that on the COC records Pertinent informa-
tion on shipment, pickup, courier, and condition of samples is entered in the ‘Remarks section. The cus-
todian then enters the sample identification tag data into a bound logbook, which is arranged by project
code and station number
/196 19 Documentation
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The laboratory custodian uses the sample Identification tag number or assigns a unique laboratory
number to each sample; the custodian transfers the samples to the proper analyst or stores them in the ap-
propriate secure area. A limited number of named individuals are allowed access to the sample storage
area. The appropriate analysts are responsible for the samples until they are returned to the custodian
When sample analyses and necessary quality assurance (OA) checks have been completed, the un-
used portIon of the sample and the sample containers must be disposed of properly (see Subsection
5 2 6.4). All identifying tags, data sheets, and laboratory records, are retained as part of the permanent
documentation.
4.6.4 Receipt-for-Samples Form
Section 3007(a)(2) of the RCRA states “if the officer, employee, or representative obtains any samples,
prior to leaving the premises he shall give to the owner, operator, or agent-in-charge, a receipt describing
the samples obtained and, If requested, a portion of each such sample equal In volume or weight to the
portion retained.” Section 104 of the Comprehensive Environmental Response, Compensation, and
Liability Act (CERCLA), as amended by the Superfund Amendments and Reauthorization Act (SARA), con-
tains Identical requirements.
Completing a receipt-for-samples form complies with these requirements: such forms should be used
whenever splits are offered or provided to the site owner, operator, or agent-in-charge. The particular form
used may vary between EPA regions: an example Is shown in Exhibit 4-3. This form Is completed and a
copy given to the owner, operator, or agent-In-charge even if the offer for split samples Is declined. The
original is given to the SM and Is retained In the project files. In addition, the contractor must provide
analytical results from the samples collected to the owner, operator, or agent In charge, as mandated in
SARA.
4.6.5 Custody Seals
When samples are shipped to the laboratory, they must be placed in padlocked containers or con-
tainers sealed with custody seals; a completed example Is shown in Exhibit 5-6. Some custody seals are
serially numbered These numbers must appear In the cross-reference matrix (Exhibit 4-1) of the field
document and on the COG report. Other types of custody seals Include unnumbered seals and evidence
tape
When samples are shipped, two or more seals are to be placed on each shipping container (such as a
cooler), with at least one at the front and one at the back, located In a manner that would Indicate if the
container were opened In transit. Wide, clear tape should be placed over the seals to ensure that seals are
not accidentally broken during shipment Nylon packing tape may be used providing that it does not com-
pletely cover the custody seal. Completely covering the seal with this type of tape may aliow the label to
be peeled off Alternatively, evidence tape may be substituted for custody seals.
If samples are subject to Interim storage before shipment, custody seals or evidence tape may be
placed over the lid of the jar or across the opening of the storage box. Custody during shipping would be
the same as described above. Evidence tape may also be used to seal the plastic bags or metal cans that
are used to contain samples in the cooler or shipping container. Sealing individual sample containers as-
sures that sample integrity will not be compromised if the outer container seals are accidentally broken.
Documentation 20 1/96
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4.6.6 Field Notebooks
A bound field notebook must be maintained by the sampling team leader to provide daily records of
significant events, observations, and measurements during field investIgations. All entries are to be signed
and dated. All members of the field investigation team are to use this notebook, which is to be kept as a
permanent record. Observations or measurements that are taken In an area where contamination of the
field notebooks may occur may be recorded in a separate bound and numbered logbook before being
transferred to the project notebook The original records are retained, and the delayed entry is noted as
such.
Field notebooks are Intended to provide sufficient data and observations to enable participants to
reconstruct events that occurred during projects and toi-efresh the memory of the field personnel if called
upon to give testimony during legal proceedings. In a legal proceeding, notes, if referred to, are subject to
cross.examination and are admissible as evidence. The field notebook entries should be factual, detailed,
and objective.
4.6.7 CorrectIons to Documentation
Unless restricted by weather conditions, all original data recorded In field notebooks and on sample
identification tags, chafn.cf-custody records, and receipt-for-samples forms are written in waterproof ink.
These accountable serialized documents are to be destroyed or thrown away, even if they are illegible
or contain Inaccuracies that require a replacement document.
if an error is made on an accountable document assigned to one person, that lndMdual may make cor-
rections simply by crossing out the error and entering the correct information. The erroneous information
should not be obliterated. Any error discovered on an accountable document should be corrected by the
person who made the entry. All corrections must be inrtiaied and dated.
For all photographs taken, a photographic log Is kept; the log records date, time, subject, frame and
roll number, arid photographer. For “instant photos,” the date, time, subject, and photographer are
recorded directly on the developed picture. The serial number of the camera and lens are recorded in the
project notebook. The photographer should review the photographs or slides when they return from
developing and compare them to the log, to assure that the log and photographs match. It can be par-
ticularly useful to photograph the labeled sample jars before packing them into shipping containers. A
clear photograph of the sample jar, showing the label, any evidence tape sealing the jar, and the color and
amount of sample, can be most useful In reconciling any later discrepancies.
4.7 REGION-SPECIFIC VARIANCES
Region-specific variances are common: the SM should contact the EPA RPM or the RSCC before any
sampling campaign to ascertain the latest procedures. Future changes In variances will be Incorporated in
subsequent revisions to this compendium.
4.7.1 RegIon I
Region I uses a standard contractor serialized chain-of-custody form and an unnumbered chain-of-cus-
tody seal, which are placed on the outside of the shipping cooler. Numbered sample bottle labels are used
for REM site work and numbered tags for FIT site work
11% 21 Documentation
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4.7.2 Region II
Region II uses an unnumbered chain-of-custody form and numbered sample bottle labels for all site
work. Custody seals are placed on the outside of the shipping cooler.
4.7.3 RegIon III
Region lii uses a senalized chain-of-custody form and numbered sampling tags. Chain-of-custody
seals used by Region III are unnumbered and placed on the outside of the shipping cooler.
4.7.4 Regfon IV
Region IV has a detailed procedural discussion in the Eng neethig Support Branch Standards Operating
Procedures and Qualily Assurance Manual, U S. EPA, Region IV, Environmental Services Division, 1 April
1986
4.7.5 RegIon V
Region V uses a serialized chain-oicustody seal. Region V seals are color coded; orange Is used for
REM and FIT work. Seals are placed on the outside of the shipping coaler only if the samples are sent the
same day as collected; otherwise, seals are placed across sample Jar lids. FIT does not note whether or
not samples were split on the chain-of-custody record. FIT Includes the corresponding Traffic Report nurn-
ber under the remarks section of the tag. The bottle lot numbers or batch numbers are not recorded
here, but on the “ChaIn-of Custody form
4.7.6 RegIon VI
Region VI does not use a serIalized number control system on custody seals
4.7.7 RegIon VII
Region VII personnel provIde onsite sample control Samples are logged Into a computer by regional
personnel. Although contractor personnel do not seal and log samples, chain ci custody Is followed as
described above.
4.7.8 Region VIII
Region VII 1 does not use a serialized number control system on custody seals
4.7.9 Region IX
Region IX does not use a serialized number control system on chain-of-custody seals
/ ) i!(! frfl1tJflOfl 22 1/96
-------
4.7.10 RegIon X
Region X does not use a serially numbered custody seal. Seals are signed, and the sample ID number
is writlen on the seal.
4.8 INFORMATION SOURCES
SuperfundAinendments and Reauthorization Act (SARA). SectIon 104(m), ‘InformatIon Gathering Access
Authontles. ’
U S. Environmental Protection Agency. NEJC Policies aiid Procedures. EPA-330/9-78-0O I -R. May 1978
(Revised February 1983)
U.S. Environmental Protection Agency. REM IV Zone Managenieiit Plan. Contract No. 68-01-7251,
CH2M HILL an U.S. EPA
U.S. Environmental Protection Agency. User’s Guide to the Contract Laboraiorj Program Office of Emer-
gency and Remedial Response. December 1986.
U S Environmental Protection Agency. Zone II REM/FIT Quahty Assurance Manual. Contract No 68-
01-6692, CH2M HILL and Hazardous SIte Control DMsion.
1/96 23 Documentation
-------
REFERENCES
U.S. EPA. 1987. Compendium of Superfund Field Operations Methods (Section 4) Documentation.
EPA/540/P-87-OO1. U.S. Environmental Protection Agency, Washington, DC.
U.S. EPA. 1991. NEIC Policies and Procedures. Revised Edition. EPA-33019-78-R. U.S.
Environmental Protection Agency, Denver, CO.
1/96 25 Docwnentation
-------
Section 5
-------
FIELD SCREENING EXERCISE
STUDENT PERFORMANCE OBJECTIVES
At the conclusion of this unit, students will be able to:
1. Screen for petroleum hydrocarbons using an enzyme
immunoassay kit.
2. Conduct a test for lead using the EM Science test strips.
3. Perform tests on water samples for copper, ammonia, and
dissolved oxygen.
4. Conduct a lead test using the LEADTRAK test kit.
5. Descnbe the operation of an x-ray fluorescence instrument.
6. Operate a pH meter to determine the pH of unknown
solutions.
7. Conduct a chlorine detection test for PCB contamination.
8. Conduct a simple hazard classification using hazard classifier
test strips on liquids.
9. Perform a lead test using lead test swabs on soil samples.
NOTE Students may use all references and material provided
in the course, unless otherwise specified, to perform
the objectives. Students are expected to perform each
objective without error.
1196
-------
FIELD SCREENING SCENARIO
Local residents have noticed dead fish in Nollan Creek (Figure 1) and have asked the stat
environmental response agency to sent a team to investigate. Because of budget constraints and
ongoing site responsibilities, only a short screening session can be scheduled at this time. The area
near where the dead fish were noted has two abandoned industrial facilities: an old battery factory
and a oil recycling facility . Both have been closed for some period of time. There are suspicions
that one or both of the facilities may be responsible for the fish kill. The task of the screening team
is to determine contaminants, possible sources, and pathways. The present owners of both facilities
have been called and permission has been given for entry and testing.
The battery factory is upstream of the recycling facility. Although there are outfalls from the plant,
there is a marked absence of vegetation on the near bank of the creek. The site is not fenced, but
the grounds have no obvious stains and the building is shuttered and locked. A concrete parking lot
surrounds the building and there are no drums or other signs of contamination. The oil recycling
facility is fenced. The grounds contain a locked cinder block building, a bermed area that appears
to have held an aboveground storage tank (AST), and a drum yard with a number of deteriorating
drums and stained soil.
The field screening plan calls for a wide variety of tests in limited numbers to achieve a broad
spectrum screening of select areas. On the first day, a soil gas survey was made over the area near
and inside the bermed area. The data will be made available. The sampling team will identify four
sites for collection of groundwater samples to be analyzed by enzyme immunoassay. These samples
will be taken with a shallow direct-push piezometer. The locations of the other samples collected
during field screening are noted on the site map.
11% 1 Field Screening Exercise
-------
Figure 1
.
Site Map
Battery Factory
Storm Sewer
Oil Recycling Facility
Cinderbiock 1<
Building I Bermed
Area
—3( X X —-X-- -X - —-X - - X X X ---X--
X X -X- Fence
D-l Drum Sample
DY-I Drum Yard Soil Sample
SB-i Stream Bank Soil or Water
Sampling Location
I
D-3
*
DY-3
*
DY-2 DY-i
t
Sampling Location
N
-------
FIELD SCREENING EXERCISE DESCRIPTION
BERMED AREA
Soil Gas
Teams will discuss the soil gas data results and determine the best location for the collection of
groundwater samples.
Enzyme Immunoassay (EIA): Four water samples
Available equipment: Millipore EIA BTEX test kit
Using the MiUipore EIA BTEX test kit, each team will analyze water samples collected from the
bermed area identified on the site map. Results will be recorded on the Field Screening Data Sheet.
STREAM BANK
Lead Test Strips: Three surface water samples (SB-i. SB-3, SB-6)
Available equipment: EM SCIENCE Lead Test Strips
Using the EM SCIENCE Lead Test Strips, each team will field screen one of three surface water
samples collected from the sampling locations identified on the site map. Results will be recorded
on the Field Screening Data Sheet.
Chemetrics®: Three surface water samples (SB-2, SB-4, SB-5)
Available equipment: Chemetrics Copper Test Kit, Chemetrics Ammonia Test Kit, Chemetrics
Dissolved Oxygen Test Kit
Using each of the three Chemetrics test kits, each team will conduct either one, two, or three of the
Chemetrics field screening tests on the three surface water samples collected from the sampling
locations identified on the site map. Results will be recorded on the Field Screening Data Sheet.
11% 3 Field Screening Exercise
-------
X-Ray Fluorescence (XRF): Three soil samples (SB-i, SB-2, SB-3)
Available equipment: XRF
Using the XRF, each team will field screen three soil samples collected from the sampling locations
identified on the site map. Results will be recorded on the Field Screening Data Sheet
pH Meter: Three surface water samples (SB-i, SB-3, SB-6)
Available equipment: pH Meter
Using the pH meter, each team will field screen each of the three samples collected from the
sampling locations identified on the site map. Results will be recorded on the Field Screening Data
Sheet
DRUM YARD
Lead I Swabs: Three soil samples (DY-i, DY-2, DY-3)
Available equipment: Lead Check Swabs
Using the lead check swabs, each team will field screen one of the three soil samples collected from
the sampling locations identified on the site map. Results will be recorded on the Field Screening
Data Sheet.
Dexsil PCB Test Kit
Available equipment: Dexsil PCB Test Kit
Using the Dexsil PCB test kit, each team will analyze one drum sample collected from one of the
three drums identified on the site map. Results will be recorded on the Field Screening Data Sheet.
SPILFYTER Test Strip
Available equipment: SPILFYTER Test Strip
Using the SPILFYTER test strip, each team will field screen one drum sample collected from one
of the three drums identified on the site map. Results will be recorded on the Field Screening Data
Sheet.
Field Screening E.rercise 4 1/96
-------
FIELD SCREENING DATA SHEET
00
D 0 = dissolved oxygen
-------
0
FIELD SCREENING DATA SHEET (cont.)
Sample jj Dexsil II
Number XRF pH Lead I PCB SPILFYTER
BERMED
AREA
2
3
4
STREAM
BANK
SB-i
SB-2
SB-3
SB-4
SB- 5
SB-6
,
DRUM
YARD
DY-i
DY—2
DY-3
0-1
D-2
D-3
-------
Section 6
-------
CONTAINERIZED
MATERIAL SAMPLING
STUDENT PERFORMANCE OBJECTIVES
At the conclusion of this unit, students will be able to:
1. Collect a legally defensible sample from containerized waste.
NOTE : Students may use all references and material provided
in the course, unless otherwise specified, to perform
the objectives. Students are expected to perform each
objective without error.
1/96
-------
OSHA REGULATIONS
CONTAINERIZED
MATERIAL SAMPLING
29 CFR Part 1910.120 (/) and Part 1926
General requirements and standards
for storing, containing, and handling
chemicals and containers
CHARACTERISTICS
• l-i gh concentrations and hazards
• Large quantities
• Multiphase layers/sludge
• Containers under pressure
1/96
I
Containerized Material Sampling
-------
METHOD SUMMARY
FSOP No. 2009
• Inventoried
• Staged
• Opened
STAGING AREA
Classify drums into:
• Rac oactive
‘Leaking
• B ging
• Labpadcs
• Explosive/shock sensitive
STAGING AREA (cont.)
Physically separate into:
• Uquids
• Solids
• Labpacks
• Cylinders
•Empty
Containerized Material Sampling 2 1/96
-------
DRUM SAMPL!NG
Under OSHA 1910.120, manual drum opening
cannot be used if contents are:
• Unknown
• Flammable
• Reactive or explosive
• Shock sensitive
METHOD SUMMARY
FSOP No. 2010
• Representative sampling
- If LEL >25%, discontinue sampling
• Can use a bailer, glass thief, sludge
judge, bacon bomb, COLlW SA, or
subsurface grab sampler
SUMMARY
• Use proper drum opening techniques
and equipment
• Use proper leveLs of protection
• Use caution
1/96 3 Containerized Material Sampling
-------
Section 7
-------
SOIL SAMPLING
STUDENT PERFORMANCE OBJECTIVES
At the conclusion of this unit, students will be able to:
1. Describe the media to be sampled.
2. List the reasons for sampling the soil on the site and in the
background location.
3. Determine which soil sampling strategy should be used in a
particular situation.
4. List and describe appropriate methods for taldng surface and
subsurface samples.
5. Determine the appropriate sample container for a soil sample
for a given analysis.
6. Operate the available soil sampling equipment in a manner
appropriate with the media and analysis requested.
NOTE : Students may use all references and material provided
in the course, unless otherwise specified, to perform
the objectives. Students are expected to perform each
objective without error.
11%
-------
SOIL SAMPLING
SOIL CONSTITUENTS
• Gravel
• Sand
• Silt
• Clay
• Organic material
SAMPLING OBJECTIVES
• Establish threat to health or environment
• Locate and identify sources
• Define extent
• Collect remedial option data
• Verify attainment of cleanup
11%
1
Soil Sampling
-------
SAMPLING STRATEGY
• Judgmental
• Random
• Systematic - grid
• Systematic - transect
Soil Sampling 2 1/9
-------
4UP 5!N!AMPLtNcL,
V
A
X Samphation .
Stained areas
Dnims
Aboveground storage tanks
Suspicious lagoon
1/96
3
Soil Sampling
-------
RANDOM SAMPLING
— 1
x
x
XSa ca X
Stain.daress -
Aboveground s ora9e tanks
;_!:3 Suspicious goon
Drums
Soi1 Sampling
4
1/9
-------
SYSTEMATIC SAMPLING
Xs Iocat t
Stained areas
) Ocums
Aboveground stofage tanks
27 Suspicious goon
-GRID
A
x
A
- x-
x
1
i- - x x’
11%
5
Soil Sampling
-------
SYSTEMATIC SAMPLING - TRANSECT
_:::::::::::X =:::::_
L
Aboveground storage tanks
:!: Suspicious legoon
Soil Sampling
1/9
¼
X Sample localion
Stained areas
‘ Drums
6
-------
SAMPLING EQUIPMENT
Surface Soil
• Trowel
• Hand auger
• Push tube
SAMPLING EQUIPMENT
Subsurface Soil
• Hollow-stem auger/s pht spoon
• Rotosonic rig
• Direct push
SAMPLE COLLECTION
_______________Volatiles
• 4-oz. wide-mouth glass jar
• Immediate transfer with some sorting
• Zero head space
• 4°C
1196 7 Soil Sampling
-------
SAMPLE COLLECTION
BNAs, PesticideslPCBs, Metals, CN
• 8-oz. wide-mouth glass jar
• Thoroughly mixed
• 80% filled
• 4°C
Soil Sa i pling 8 1/9
-------
MEDIUMTO I I SILTYSAND
COARSE SAND
SAMPLE LOCATION
B 1.1 mg/kg
3.0
____ SANDY SILT ____ CONTAMINATED CLAY
AREA
0
m
-u
—1
I
m
0
5
10
15
20
25
30
35
C /)
-I
m
C)
:ij
0
C l)
C’)
C’)
m
C)
H
0
z
V
WATER TABLE
-------
0 ORGANICS
SINKHOLE
HOWE VALLEY NPL ShE
SAMPLING LOCATIONS
FOR ORGANICS
3 ft. - tetrachioroethene conc.
(mg/kg)
D
0
Cl)
-I
C)
• METALS
X TCL ANALYSIS
-------
REFERENCES
U.S. EPA. 1989. Methods for Evaluating the Attainment of Cleanup Standards: Volume 1—Soils
and Solid Media. EPA/230/02-89-042. U.S. Environmental Protection Agency, Office of Policy,
Planning, and Evaluation, Statistical Policy Branch, Washington, DC.
U.S. EPA. 1991a. Compendium of ERT Soil Sampling and Surface Geophysics Procedures.
EPA/540/P-91-006. U.S. Environmental Protection Agency, Office of Emergency and Remedial
Response, Environmental Response Team, Washington, DC.
U.S. EPA. 1991b. Removal Program, Representative Sampling Guidance: Volume 1—Soil.
Interim Final. PB 92-963408. OSWER Directive 9360.4-10. U.S. Environmental Protection
Agency, Washington, DC.
U.S. EPA. 1992. Guidance for Data Useability in Risk Assessment (Part A). Final Report. PB
92-963356. OERR Publication 9285.7-09A. U.S. Environmental Protection Agency, Washington,
DC.
U.S. EPA. No date. Summary of Remedial Alternative Selection: Record of Decision, Howe
Valley Landfill, Howe Valley, Kentucky. U.S. Environmental Protection Agency, Region 4,
Atlanta, GA.
1/96 11 Soil Sampling
-------
Section 8
-------
SURFACE WATER AND
SEDIMENT SAMPLING
STUDENT PERFORMANCE OBJECTIVES
At the conclusion of this unit, students will be able to:
1. Describe the media to be sampled.
2. List the reasons for sampling the surface water and sediment
on the site and in the background location.
3. Determine which surface water sampling strategy should be
used in a given situation.
4. Determine which sediment sampling strategy should be used
in a given situation.
5. List arid describe appropriate methods for obtaining surface
water samples.
6. List and describe appropriate methods for obtaining sediment
samples.
7. Determine the appropriate sample container and preservative
for surface water samples for a given analysis and for
sediment samples for a given analysis.
8. Operate the available surface water and sediment sampling
tools.
NOTE : Students may use all references and material provided
in the course, unless otherwise specified, to perform
the objectives. Students are expected to perform each
objective without error.
1/96
-------
SURFACE WATER AND
SEDIMENT SAMPLING
SEDIMENT
Any inorganic and organic
material transported and
deposited by water
SURFACE WATER BODY TYPES
• Freshwater-flowing
• Freshwater-standing
• Saltwater
• Estuaries
Suiface Water and
1/96 i Sediment Sampling
-------
PURPOSE OF SURFACE WATER
AND SEDIMENT SAMPLING
• Contaminants can be transported
by surface water
• Sediment is “end of the line”
for many contaminants
SURFACE WATER
SAMPLING LOCATION
AND EQUIPMENT
IN-SITU WATER QUALITY
PARAM ETERS
• Temperature
•pH
• Dissolved oxygen
• Oxidation/reduction potential
• Conductivity
Surface Water and
Sediment Sampling 2 1/96
-------
LAKE STRATIFICATION
kit
Summer
1 DO!
olimnion
De th (J
Temperature(°C)/D.O.
Winter
Depth!
Tempo rature (°C)/D.O.
rmocline
FLOWING SURFACE WATER
Surface Water and
I, I , I ,
• Sampling
location
1/96
3
Sediment Sampling
-------
SURFACE WATER SAMPLING
Direct Method
• Immerse with mouth of bottle upstream
• Do not disturb sediment
• Use caution if bottles are prepreserved
SURFACE WATER SAMPLING
Other Methods
• Sample pumps - peristaltic pump
• Extended rod, dip sampler
• Messenger release - beta, kemmerer,
bacon bomb
Surface Water and
Sediment Sampling 4 1/96
-------
GRAB VS. COMPOSITE SAMPLING
Individual Grabs
Composited Grabs
Su,face Water and
SITE
Left Right
Channel Midstream Channel
1/96
5
Sediment Sampling
-------
SEDIMENT
SAMPLING LOCATION
AND EQUIPMENT
SEDIMENT SAMPLING LOCATIONS
Stream Morphology
Riffle
Pool
Flow
Riffle
Pool
Riffle Dam
L Riffle
Deposited Material
Obstruction
‘face Waler and
.i nt Sampling 6 1/96
-------
SEDIMENT TRANSPORT
Variables
• Particle size distnbution
• Organic carbon content
SEDIMENT TRANSPORT
Particle Size
• Boulders -Basketball or bigger
• Cobble - Grapefruit
• Gravel - Pea to orange
• Sand - Sugar to rock salt
• Silt - Flour
• Clay - Talcum po er
SEDIMENT SAMPLING EQUIPMENT
Corers
• Free-fall corers
• Hand corers
• Push tubes
Suiface Water and
1/96 7 Sediment Sampling
-------
SEDIMENT SAMPLING EQUIPMENT
Grabs
• Ekman
• Ponar
• Augers
Surface Water and
Sediment Sampling 8 1/96
-------
CONTAINERS RECOMMENDED
FOR SURFACE WATER
• Volatiles Two 40-mi vials with Teflon®-lined
septum caps
Preservative: 4 drops concentrated HCL
Cool to 4°C
• Semi- One 1-gallon or two 1/2-gallon amber
volatiles glass with Teflon® liner
Preservative: Cool to 4°C
• Pesticides/ One 1-gallon or two 1/2-gallon amber
PCBs glass with Teflon® liner
Preservative: Cool to 4°C
CONTAINERS RECOMMENDED
FOR SURFACE WATER (cont.)
• Metals One 1-L polyethylene with
polyethylene-lined closure
Preservative: Nitric acid to pH < 2
Cool to 4°C
• Cyanide One 1-L polyethylene or one 1/2-gallon
polyethylene with polyethylene or
polyethylene-lined closure
Preservative: NaOH to pH> 12
Cool to 4°C
Su ace Water and
1/96 9 Sediment Sampling
-------
CONTAINERS RECOMMENDED FOR
SEDIMENT SAMPLES
• Volatiles 4-oz. wide-mouth glass jar
• Semivolatiles 8-oz. wide-mouth glass jar
• Pesticides/PCBs 8-oz. wide-mouth glass jar
• Metals 8-oz. wide-mouth glass jar
• Cyanide 8-oz. wide-mouth glass jar
or I 6-oz. (500-mI) polyethylene jar
• Preservatives: Cool to 4°C
Suiface Water and
Sediment Sampling 10 11%
-------
SAM PLI NC
Stainless
Ponar
Ponar
Dredge
/ Beta
/ ,/Sampler
Sewage
Sampler
S eI Bucket Peristaltic Beta
Pum Sanipler
Shallow/Fast water
Deep/Standing water
-------
REFERENCES
Lind, O.T. 1979. Handbook of Common Methods in Lirnnology. Second Edition. The CV.
Mosby Co., St Louis, MO
U S. Bureau of Reclamation. 1991. Quality Assurance Guidelines for Water Quality Investigations.
U.S. EPA. 1973. Handbook for Monitoring Industrial Wastewater. PB-259146. U.S.
Environmental Protection Agency Technology Transfer, National Technical Information Service,
Springfield, VA.
U.S EPA. 1991. Region IV Engineering Support Branch Standard Operating Procedures and
Quality Assurance Manual. U.S. Environmental Protection Agency, Athens, GA.
U.S Geological Survey 1989. Methods for Collection and Analysis of Aquatic Biological and
Microbiological Samples. Techniques of Water-Resources Investigations of the U.S.G.S. Book 5,
Chapter A4 U.S Geological Survey, Reston, VA.
Surface Water and
1/96 13 Sediment Sampling
-------
Section 9
-------
GROUNDWATER SAMPLING
STUDENT PERFORMANCE OBJECTIVES
At the conclusion of this unit, students will be able to:
1. Describe the media to be sampled.
2. List the reasons for sampling the groundwater on the site
using existing or new monitoring wells.
3. Determine which groundwater sampling strategy should be
used in a particular situation.
4. List and describe the appropriate procedures for taking
groundwater samples.
5. Determine the appropriate sample container and preservative
for a groundwater sample for a given analysis.
6. Operate the available groundwater sampling equipment in a
manner appropriate with the analysis requested.
NOTE : Students may use all references and material provided
in the course, unless otherwise specified, to perform
the objectives. Students are expected to perform each
objective without error.
1/96
-------
GROUNDWATER
SAMPLING
GROUNDWATER
Subsurface water that occurs
below the water table
in fully saturated unconsolidated
and/or consolidated aquifers
BASIC PROPERTIES OF AQUIFERS
• Porosity
• Permeability
1/96 1 Groundwater Sampling
-------
POROSITY:
PERMEABILITY:
OPENINGS
CONNECTIONS
cz . .
‘ ‘ 2 i
\•
-
BASIC GROUNDWATER
PARAMETERS
•pH
• Temperature
• Conductivity
• Redox potential
• Turbidity
GROUNDWATER
•
COLLECTION
Monitoring wells
•
Piezometers
•
Groundwater production wells
•
Sumps
•
Direct push or open boreholes
]
2
Groundwater Sampling
1/96
-------
MONITORING WELL
• Specifically constructed
• Represents particular aquifer or
particular zone within aquifer
• Allows collection of defensible
groundwater sample
PURPOSE OF SAMPLING
GROUNDWATER
• Determine groundwater quality
• Indicate contaminant release
• Identify contaminant
• Indicate contaminant migration
GROUNDWATER SAMPLING
STRATEGY
Determine opumum sampling location:
• Use existing wells
• Place new wells
1/96 3 Groundwater Sampling
-------
MONITORING WELL DESIGN
Must be properly constructed to sample
target contaminant(s). Consider the
following:
• Well depth
• Screen depth
• Screen length
COLLECTION OF
GROUNDWATER SAMPLES
MONITORING WELL
Groundwater Sampling
4
1/96
-------
SAMPLING PROCEDURE
• Record water level, water parameters,
and depth of well
• Calculate water volume in well
• Purge well
• Determine collection order
• Determuie collection equipment
• Place rn containers with preservatives
WATER LEVEL MEASUREMENT
EQUIPMENT
• Steel tape with chalk
• Electtic sounders
• Interface probe
WELL WATERVOLUME
CALCULATION
• 2
Water column (Well radius) 0.163
(in feet) (in inches) (conversion)
Water volume
(in gallons)
1/96 5 Groundwater Sampluig
-------
WELL PURGING
A Compendium of Superfund Field Operations
Methods, 1987
• Common procedure: Three to five
well volumes
• Reliable method: Stability of water
parameters (temperature, pH,
conductivity) over three well volumes
SAMPLE COLLECTION ORDER
1. Volatile organics
2. Extractable organics
Base/neutral acid extractables (BNAs)
Pesticides/PCBs
3. Total metals
4. Dissolved metals (if applicable)
5. Cyanide
SAMPLE COLLECTION EQUIPMENT
• Submersible pump (FulLz or Grunfos)
• Bladder pump
• Bailers
• Inertial pump (Waterra)
• Direct push
C ’ ounthva:er Sampling 6 1196
-------
SAMPLE CONTAINER AND
PRESERVATIVE
• VolatUes Two 40-mi vials with Teflon®-lined
septum caps
Preservative: 4 drops concentrated HCL
Cool to 4°C
Holding time: 14 days
• Semi- One 1-gallon or two 112-gallon amber
volatUes, glass with Teflon® liner
Pesticides, Preservative: Cool to 4°C
and PCBs Holding time: 7 days extraction
40 days analysis
SAMPLE CONTAINER AND
PRESERVATIVE (cont.)
• Metals One 1-L polyethylene with polyethylene-
lined closure
Preservative: Nitric acid to pH <2
Cool to 4°C
Holding time: 6 mo. (mercury 28 days)
• Cyanide One 1-L polyethylene or one 1/2-gallon
polyethylene with polyethylene or
polyethylene-lined closure
Preservative: NaOH to pH> 12
Cool to 4°C
Holding time: 14 days
1/96 7 GroI nd water Sampling
-------
FIELD FILTERING
• Follow standard operating procedures
(SOPS)
• Used for dissolved inorganics
• Not used for:
- lox (total organic halogens)
- TOC (total organic carbon)
- Organic analysis
Groundwater Sampling 8 1/96
-------
REFERENCES
U.S. EPA. 1986. Resource ConservatLon arid Recovery Act (RCRA) Ground-Water Monitoring
Technical Enforcement Guidance Document. EPA/600/2-85/104. U.S. Environmental Protection
Agency, Washington, DC.
U.S. EPA. 1992. RCRA Ground-Water Monitoring: Draft Technical Guidance. EPAI54O-R-93-
001. U.S. Environmental Protection Agency, Washington, DC.
1/96 9 Groundwater Sampling
-------
Section 10
-------
FIELD EXERCISE
STUDENT PERFORMANCE OBJECTIVES
At the conclusion of this unit, students will be able to:
1. Sample groundwater, soil, sediment, surface water, and
containerized waste using the proper tools and techniques.
2. List the appropriate sampling equipment according to media
and the advantages and disadvantages of each.
3. Properly label all types of sample containers.
4. Correctly complete the chain of custody for each collected
sample.
NOTE : Students may use all references and material provided
in the course, unless otherwise specified, to perform
the objectives. Students are expected to perform each
objective without error.
1/96
-------
FIELD EXERCISE DESCRIPTION
STATION ONE: SOIL SAMPLING
The following equipment is available:
Bucket augers Stainless steel pans
Hand trowels Sieves
Each team will collect one grab sample for semivolatile analysis and one grab sample for volatile
analysis Each team will collect samples in accordance with ERT’s FSOP #2012, Soil Sampling.
STATION TWO: FIELD DECONTAMINATION
The following equipment is available.
Isopropyl alcohol Brushes
Buckets Detergent and water
Spray and squirt bottles Aluminum foil
Catch basins
Each team will field decontaminate at least two different pieces of sampling equipment from the soil
and/or groundwater sampling station. Each team will collect a field blank for volatiles in accordance
with ERT’s FSOP #2006, Decontamination.
STATION THREE: SURFACE WATER AND SEDIMENT SAMPLING
The following equipment is availabIe
LaMoue sampler Ponar dredge
Bacon bomb Peristaltic pump
Kemmerer sampler Hand auger
Gravity corer Beta sampler
Ekman dredge
Each team will collect a grab sample of surface water for cyanide analysis and a sediment sample
for metals analysis. Each team will collect samples in accordance with ERT’s FSOP #2013, Water
Sampling, and FSOP # 2016, Sediment Sampling
1/96 1 Field Exercise
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STATION FOUR: GROUNDWATER SAMPLING
The following equipment is available:
Water-level indicator Bailers
Bladder pump Peristaltic pump
p11 meter Waterra pump
Each team will collect two 40-mL vials for volatile analysis from Monitoring Wells 1 and 3 and take
water level and pH measurements from the appropriate well. Each team will use the water-level
indicator in accordance with ERT’s FSOP # 2115, Water-Level Measurements, and samples will be
collected in accordance with ERT’s FSOP #2007, Groundwater Sampling.
STATION FIVE: CONTAINERIZED WASTE SAMPLING
The following equipment is available:
COLIWASA Drum thief
Bacon bomb Bung wrenches
I-land trowel Dip stick
Each team will collect representative samples from the drums for pesticides/PCB analysis and BNAs.
Each team will collect samples in accordance with ERT’s FSOP #2009, Drum Sampling.
F e1d Exerc: e 2 1/96
-------
PROJECT NO x i i r x J PROJECT LEADER
REMARKS
PROJECT NAME/LOCATION
SFHM OUI
SAMPLE TYPES
I JRFACE TE6 6 SO1L/OEDII4ENI
2 CR U4MI R I SLI.OCL
I POTABLI Vl *TER A 1’aRSTE
4 5I4ASIE TER 6 MR
A LO4ATE 10 FISH
II OTH R_ —
SAMPLERS (SIGN)
ANALYSES
U)
,% ARKS
LAB
2
USE
ONLY
.?
w
0.
“ 19_
a
STATION NO DATE
TIME
8
STATiON LOCATION/DESCRIPTION
RELINQUISHEOBY
(PRINT)
DATE/TIME RECEWEDBY
(PRINT)
(SIGN)
RELJNQU 1EDBY — — —
(PRINT)
DATE/TIME
RECEIVEDBY
(PRINT)
(SIGN)
(SJGN)
(SIGN)
RELINQUISIIEOBY
(PRINT)
DATE/TIME RECEIVED BY
(PRINT)
(SIGN)
RELINQLIISHEDBY
(PRINT)
DATE/TIME
RECEIVED BY
(PRINT)
(SIGN)
(SIGN)
(SIG N)
-------
INDIVIDUAL DRUM LOG SHEET
Job #_________________ Date
Page_____ of_____
Client
Drum #
Sample U.
Drum Size:
o 85 Gallon
o 15 Gallon
o 55 Gallon
0 5 Gallon
0 42 Gallon
0 Other
0 30 Gallon
Type of Drum: 0 FIber 0 Poly 0 Steel o Open o light Other___________
Top Head
Description of Sample: HNU Reading_________________________
LAYER 1 (TOP)
Color
0 Uquid
0 Solid
Amount (In)
0 Sludge
LAYER
2 (MIDDLE)
Color_______________________
0 Uquid
Amount
0 Solid
(in)____________
0 Sludge
LAYER
3 (BOTTOM)
Color________________________
0 Uquld
Amount
0 Solid
(in)____________
0 Sludge
Amount in Drum: 0 Empty (c iN residuals)
0 1/4 0 1/2 0 3/4 0 Full
=============== =====================—=====——========== == =
Description of Drum (Drum Label, Markings and Conditions): Overpack Needed? 0 Yes 0 No
Compatibility Group:
lime__________
R,v /1$/
Composite NumberS
tAJl .. e
Sampled by
AM-O4-CP4 .l-O
-------
PROBLEM SESSION: SAMPLE PLAN
DEVELOPMENT EXERCISE
STUDENT PERFORMANCE OBJECTIVES
At the conclusion of this unit, students will be able to:
1. List the elements of a phased sampling plan.
2. Perform the initial elements of a sampling event from
background data analysis through field data point selection,
collection, and analysis.
NOTE Students may use all references and material provided
in the course, unless otherwise specified, to perform
the objectives. Students are expected to perform each
objective without error.
11%
-------
Sample Plan Development Exercise
American Creosote Works, Inc., Winnfield, Louisiana
PROJECT OBJECTIVE
Your environmental consulting firm, ______________________, has been contracted by the U.S.
Environmental Protection Agency (EPA) to develop a sampling plan for the American Creosote
Works, Inc (ACWI) facility. The site may be evaluated using background data (Phase I), field
screening techniques, and some limited sampling of water and sediment (Phase II). Finally, your
firm is to outline in a class presentation its recommendations of further sampling points, including
monitoring wells.
PROJECT SCOPE
Phase I: Background Data Search
Objective: Determine initial areas of interest for the screening phase and begin to
“build” a site conceptual model
You will do a thorough background search using the information provided and the cost of obtaining
this information will be subtracted from your total budget for Phases I and II. This information will
assist you in establishing the objectives for the remaining phases of the project. Phase I will include
a site walkover and a review of available topographic maps, aerial photographs, and general geologic
in formation.
Phase II: Selection and Implementation of Field Screening Techniques
Objective: Determine general areas of contamination, contaminant movement, and
media of concern
After choosing the field screening technique, level of analytical support, and location of sampling
points, visit the instructors at the “data table” and purchase your field data. Your Phase II budget
is $27,000. You may not exceed your budget. Phase II should be broken down into discrete
sampling events as if the sampling were proceeding on a day-by-day basis. In other words, get a
few boring logs and some soil gas data, review the results, and then decide where to sample next.
Do not wait until the end of Phase II to get the majority of the data. Doing so defeats the
immediate feedback aspect of field screening.
1/96 1 Problem Session
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The available field screening data consist of
• Soil gas data collected from four 0 25-acre contiguous blocks.
• Geologic logs for soil borings to 10 ft below the surface.
• Field laboratory analysis of sediment samples collected from surface to 6 In. below
surface
• Field laboratory analysis of surface water samples.
• Field laboratory analysis of groundwater samples collected using a direct-drive well
point (average groundwater depth is 12 ft below the surface).
Each group should chose the type of sample and sample location. The sample location should be
marked on the gridded map provided To obtain data, present the map at the data table and the data
will either be provided on the map or as a separate analytic sheet In some cases, computer work
stations wilE be available to obtain data The data can be obtained by following the menu on the
computer screen. Analytical worksheets will be provided to record analytical information found on
the computer screen A U the data points except the soil gas 0.25-acre soil gas blocks need an
identification number, such as SB-i or SED-5, so that the data from that location can correspond to
the data sheet.
Phase Ill: Development of a Sampling and Analysis Plan
Objective: Determine specific chemicals and their concentrations in each media,
delineate areas and volumes of contamination for each media, and track movement
of the contaminants in each media
Evaluate your preliminary data from Phases I and II and develop a sampling and analysis plan for
the next step in the ACWI site investigation The primary focus of this phase is to use the findings
from the background and screening phases to characterize the site. The specific sampling objectives
by media will be provided. Select the sample locations, media, analytical support level, procedures,
etc. Record the costs and present the final estimate with the sample locations in Phase IV.
Phase IV: Results and Conclusions
Each group will present their sampling and analysis plan (as well as any conclusions and
recommendations) to the class. Choose a spokesperson to present your firm’s efforts. By preparing
this presentation, you will have to organize your findings, develop a reasonable conceptual model,
and make your recommendations understandable to someone outside your group. Though a rough
budget should be presented, this is not an exercise in finding the low bidder. The presentation
should concentrate on the proposed sampling locations; the screening phase should be covered only
in presenting the conceptual model Do not present your Phase H field screening locations.
Problem Session 1/96
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BUDGET WORKSHEET
Phase I: Background Data Search
Phase II: Selection and Implementation of Field Screening Techniques
These are the costs to be used for the field screening activities. Data should be collected in a phased
fashion. Obtain some boring and soil gas data and analyze these data in relation to your firm’s
conceptual model Then, gather more data to expand an area of interest or perhaps find a new area
of contamination.
Mobilization fee (one-time charge) $3000.00 $3000.00
Ambient air monitoring
for entire site using OVA-128,
GC mode, tentative
identification (one-time charge) $1000.00 $1000.00
Shallow soil boring,
stratigraphic identification $500.00 ea.
Soil gas survey in
four 0 25-acre blocks $500.00/acre
Water analysis of drive points
(Volatiles [ VOAs] and base/neutral acid
extractables [ BNAs] only) $500.00/point
Surface water analysis $500.00/sample
VOAs and BNAs only
Sediment sample analysis $500.00/sample
VOAs and BNAs only
This price schedule does not take into account any surcharge for higher levels of protection than
Level D IMPORTANT: You must review the air monitoring survey before any other work is
performed on the site. This will allow you to make a determination of the level of protection
appropriate for the site However, no surcharge for higher levels of protection will be added at this
time The optimum use of field screening techniques is to get some data and then make informed
decisions on where to proceed to obtain more data.
TOTAL BUDGET FOR PHASE II = $27,000.00
1/96 3 Problem Session
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BUDGET WORKSHEET
Phase Ill: Development of a Sampling and Analysis Plan
Phase IV: Results and Conclusions
Your recommendations will include some of the following analytical support. The prices provided
must be used to approximate the cost of your recommendations (these lab prices include taking the
sample in the field). Calculate the amount spent on each phase, particularly the cost of your Phase
III sampling effort. This number will be part of the Phase IV presentation.
Data interpretation,
report preparation $30,000.00 $30,000.00
VOAs $450.00
BNAs $80000
Pesticides/PCBs $500.00
Total inorganics $700.00
Benzene, toluene, ethyl-
benzene, and xylenes
(BTEX) $150.00
Special analyses
(ask instructor for price)
Exploratory borings $100.00/ft
Monitoring wells
Drilling costs plus $1000.00
Heavy equipment
Geophysical surveys
Problem Session 4 J/96
-------
Drilling and sampling will be $100.00/ft. To construct a monitoring well in the boring, add
$1000.00 for materials and installation. Again, no surcharge will be assessed for increased levels
of protection (above Level D). However, you must determine what level of protection is
appropriate. Be sure to include the appropriate number of quality assurance and quality control
samples and their cost. Figure an additional 10% surcharge to complete the chain-of-custody
paperwork and properly package the samples for shipment.
The budget for phase III is not set, your firm will determine the necessary activities and calculate
the cost, Any activities not listed above that are deemed appropriate or equipment not listed may
be included. If a price is needed ask an instructor and a reasonable estimate will be provided. Use
your imagination and experience and the class resources to determine the necessary activities and
include them in the final sampling plan.
TOTAL BUDGET FOR PHASE Ill
1/96 5 Problem Session
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PHASE I: BACKGROUND DATA
Louisiana Department of Environmental Quality Files
The Louisiana Department of Environmental Quality (LDEQ) had reports of potential waste
management problems at the ACWI site in Winnfield. LDEQ issued a Compliance Order 2 years
previous. Last year, LDEQ found the site abandoned arid the case was referred to EPA. EPA is
the now the lead agency on the environmental assessment and, as such, all pertinent file information
has been transferred to EPA.
U.S. Army Corps of Engineers’ Files
The U.S. Army Corps of Engineers’ files show no record of an application by American Creosote
Works, Inc. (ACWJ) to fill, build upon, or otherwise alter a wetland. No further information is
available regarding ACWI.
Louisiana Geological Survey
Winrifield, Louisiana, is within the Mississippian-age section of the Gulf Coastal Plain. Deposits
in this region consist mainly of braided stream channel deposits (sand, silts, and clays with associated
interspersed gravel).
The ACWI facility is located on the Cockfield Formation. This formation was deposited during the
Tertiary Period (65 to 10 million years before present). It consists primarily of interbedded clays,
silts, and sands with significant lignite (a brownish-black coal that is intermediate in coalification
between peat and a subbiturninous coal) deposits.
Soil Conservation Survey Data
The Soil Conservation Service (SCS) survey for the area is incomplete at this time. Preliminary data
indicate that the soil type is composed of fine-grained, organic-rich material characteristic of flood
plain or marsh deposits. The available report is in the brown folder along with a set of aerial
photographs.
Information from the Chamber of Commerce
The ACWI site has been operating under various names and owners in this location since 1901. It
has been the site of wood-preserving operations since approximately 1910, when it was bought by
the Louisiana Creosoting Company. The site has operated as a wood-preserving facility by various
entities over the years. The present owners bought the site in 1980. The major product lines in
recent years have been telephone poles and railroad ties.
Problem Session 6 1196
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State of Louisiana Water Supply Board Files
The State of Louisiana Water Supply Board files indicate that there are no known residential supply
wells in the vicinity of the ACWI site The wells for the City of Winnfield are screened in The
Sparta Formation at a depth of about 600 ft below ground surface. The nearest municipal well to the
site is the Red Hill Well located about 4000 ft east-southeast of the site. The other wells are located
farther than a mile from the site to the north.
Information from the Tax Assessor’s Office
ACWI is located in the town of Winnfield, Louisiana, Winn Parish, on a small access road. It is
near several major truck routes and railroad lines. Al! taxes are currently paid.
The property consists of 34.21 acres, two large and three small buildings, as well as fifteen above
ground vertical storage tanks and five pressure treatment vessels.
Climatological Data
The climate in Winnfield, Louisiana, is subtropical. The average temperature (from 1951 to 1980)
ranges from 47F in January to 81 in July and August The average net annual rainfall is 50 in.
The heaviest rainfall is in April and May and the lightest is in October. Tropical storms and
hurricanes occasionally pass through the area. Flood-producing rains may occur during any month
of the year.
Historical precipitation data:
2yr3Omin 1.7in.
10 yr 30 mm 2.4 in.
100 yr 30 mm 3.5 in.
2yrlhr 2.2in.
l0yr lhr 3m.
lOOyr lhr 4in.
2yr6hr 3.5in.
10 yr 6 hr 5.5 in.
lOOyr6hr 8in.
2 yr 24 hr 4.5 in.
10 yr 24 hr 8.5 in.
100 yr 24 hr 11 in.
Mean annual lake evaporation is 48 in.
1/96 7 Problem Session
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Interview with Local Residents
The local fire department was contacted to determine whether any fire-related problems had been
attributed to the facility. Fire department records did not indicate that any fires had occurred at the
facility. Mr. Mercer, the fire chief, did recall that the fire department had been asked to provide
help at the publicly owned treatment works (POTW) to remove siltation within one of the
construction areas. Sediments from Creosote Branch had backwashed into one of the concrete basins
under construction and needed to be removed. During removal, members of the construction crew
experienced blistered skin and breathing difficulties. Creosote was reportedly smelled. Mr. Mercer
did not know whether anyone had received medical attention for injuries specific to the removal
efforts.
Hydrologic Information
The groundwater table in the vicinity of the site is shallow, as indicated by the numerous marshy
areas surrounding the site. At the site, groundwater was encountered within 10 ft of the ground
surface. Using a limited number of data points in the area, the near-surface aquifer flow direction
and velocity were estimated using the triangulation method and Darcy’s Law. The direction of
groundwater flow is generally to the north in the area of the site. Groundwater seepage velocity is
approximately 0.9 feet per day.
The local residents are all on city water, which is obtained from four wells. Each of the wells is
screened in the Sparta Sand Formation. Water analysis shows no contaminants in the water supply
at this time
Problem Session 8 1/96
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U.S. ENVIRONMENTAL PROTECTION AGENCY
The ACWI site is located in Winn Parish, in the town of Winnfield, Louisiana, and is a part of the
flood plain of the Mississippi River. The region is heavily forested, primarily with tall, standing
white pines and some cedar. It is located within easy access to several truck routes and railroad
lines. The property is relatively fiat, with a total relief of 19 ft Drainage is to the north and east
into Creosote Branch and is enhanced by the presence of two major drainage ditches (Figure 1).
Access to the site is limited, largely due to the surrounding wetlands and heavily forested areas. In
August 1989, a perimeter reconnaissance of the site was performed. At the time of the
reconnaissance, several storage tanks were present at the facility There was a large (approximately
100 ft by 300 ft) tar stain on the ground surface in the eastern portion of the site. In addition to the
stained area, three areas of disturbed soil were reported by former workers in the north, central, and
southern portions of the site, however, the reconnaissance team was unable to visually locate the
three areas. It is suspected that these areas were covered with clean soil to conceal old tar pits. Five
buildings were present on the site One was used for offices and administration, one was used as
a laboratory, and the others were used for industrial processing Five large pressure vessels (PV)
were present in the processing buildings. Some soil staining was observed around the pressure
vessels. -
Wetland habitats in the area include emergent palustrine wetland near the tar area containing rushes,
reeds, and dead maple trunks. Creosote Branch becomes a freshwater wetland 1 km downstream of
the site, and remains a wetland for the next 15 miles. The forested areas are concentrated on the
eastern portion of the site and extend from the Creosote Branch south along the eastern edge of the
tar area and around the pond. Vegetation in the forested area is characteristic of the loblolly-slash
pine forest common in the southeastern United States, A large portion of the site is open or
disturbed by prior industrial activity. When these areas are vegetated, they are dominated by grasses
and herbs
Ambient air monitoring of the site indicated elevated levels of volatile organic compounds, with the
highest levels in the vicinity of the surface tar area.
A memorandum from a chemical engineer whose specialty is process design was found in some
onsite files It stated that compounds that might be expected at a wood preservative plant include,
but are not limited to, naphthalene, 2-methylnaphthalene, 1-methylnaphthalene,
2,6-dimethylnaphthalene, pentachiorophenol, phenanthrene, anthracene, fluoranthene, pyrerie,
benz(a)arithracene, chrysene, benzo(b)fluoranthene, ben.zo(a)pyrene, indeno(1 ,2 ,3-cd)pyrene, and
several different volatile organic compounds. Other records found onsite gave some information
about the magnitude of the operation. For a 7-month period ending July 31, 1966, more than
750,000 gallons of petroleum distillate, 40,000 gallons of creosote, and 54,000 pounds of
pentachiorophenol were used to treat approximately 7.5 million board-feet of wood. After 1981,
however, the site was purchased after the previous site owner declared bankruptcy. The new owner
ran the operation on a much smaller scale than the 1960s operation.
1/96 9 Problem Session
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‘1
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Grove Street
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Approx*’n ate Scale
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LEGEND
A Fo ested Area
LI Residence
LIII Building/PV
• Vertical Tank
Woodchip Pile
-------
United States
Environmental Protection
Agency
Office of Emergency and
Remedial Response
Washington, DC 20460
Publication 9360.4-10
PB92-963408
November 1991
EPA
Removal Program
Representative Sampling
Guidance
Volume 1 -
Soil
-------
United States
Environmental Protection
Agency
Superfund
Office of Emergency and
Remedial Response
Washington. DC 20460
Compendium of ERT
Groundwater Sampling
6EPA
-------
GENERAL FIELD
SAMPLING GUIDELINES
SOP# 20O .
DATE 08/11/94
REV.# 00
1.0 SCOPE AND APPLICATION
The purpose of this Standard Operating Procedure
(SOP) is to provide general field sampling guidelines
that will assist REAC personnel in choosing sampling
strategies, location, and frequency for proper
assessment of site characteristics This SOP is
applicable to all field activities that involve sampling
These are standard (i e., typically applicable)
operating procedures which may be varied or changed
as required, dependent on site conditions, equipment
limitations or limitations imposed by the procedure In
all instances, the ultimate procedures employed should
be documented and associated with the final report
Mention of trade names or commercial products does
not constitute U S EPA endorsement or
recommendation for use
2.0 METHOD SUMMARY
Sampling is the selection of a representative portion of
a larger population, universe, or body Through
examination of a sample, the characteristics of the
larger body from which the sample was drawn can be
inferred In this manner, sampling can be a valuable
tool for determining the presence, type, and extent of
contamination by hazardous substances in the
environment
The primary objective of all sampling activities is to
charactenze a hazardous waste site accurately so that
its Impact on human health and the environment can
be properly evaluated Itis only through sampling and
analysis that site hazards can be measured and the job
of cleanup and restoration can be accomplished
effectively with minimal risk The sampling itself
must be conducted so that every sample collected
retains its original physical form and chemical
composition In this way, sample integrity is insured,
quality assurance standards are maintained, and the
sample can accurately represent the larger body of
matenal under investigation
The extent to which valid inferences can be drawn
from a sample depends on the degree to which the
sampling effort conforms to the project’s objectives
For example, as few as one sample may produce
adequate, technically valid data to address the
projects objectives Meeting the project’s objectives
requires thorough planning of sampling activities, and
implementation of the most appropriate sampling and
analytical procedures These issues will be discussed
in this procedure
3.0 SAMPLE PRESERVATION,
CONTAINERS, HANDLING,
AND STORAGE
The amount of sample to be collected, and the proper
sample container type (i e , glass, plastic), chemical
preservation, and storage requirements are dependent
on the matrix being sampled and the parameter(s) of
interest Sample preservation, containers, handling,
and storage for air and waste samples are discussed in
the specific SOPs for air and waste sampling
techniques
4.0 INTERFERENCES
POTENTIAL PROBLEMS
AND
The nature of the object or materials being sampled
may be a potential problem to the sampler If a
matenal is homogeneous, it will generally have a
uniform composition throughout In this case, any
sample increment can be considered representative of
the material On the other hand, heterogeneous
samples present problems to the sampler because of
changes in the material over distance, both laterally
and vertically
Samples of hazardous materials may pose a safety
threat to both field and laboratory personnel Proper
health and safety precautions should be implemented
when handling this type of sample
-------
Environmental conditions, weather conditions, or
non-target chemicals may cause problems andlor
interferences when performing sampling activities or
when sampling for a specific parameter Refer to the
specific SOPs for sampling techniques
5.0 EQUIPMENT/APPARATUS
The equipment/apparatus required to collect samples
must be determined on a site speetfic basis Due to the
wide variety of sainpluig equipment available, refer to
the specific SOPs for sampling techniques which
include lists of the equipment/apparatus required for
sampling
6.0 REAGENTS
Reagents may be utilized for preservation of samples
and for decontamination of sampling equipment The
preservatives required are specified by the analysis to
be performed Decontamination solutions are
specified in ERT SOP #2006, Sampling Equipment
Decontamination
7.0 PROCEDURE
7.1 Types of Samples
In relation to the media to be sampled, two basic types
of samples can be considered the environmental
sample and the hazardous sample
Environmental samples are those collected from
streams, ponds, lakes, wells, and are off-site samples
that are not expected to be contaminated with
hazardous materials They usually do not require the
special handling procedures typically used for
concentrated wastes However, in certain instances,
environmental samples can contain elevated
concentrations of pollutants and m such cases would
have to be handled as hazardous samples
Hazardous or concentrated samples are those collected
from drums, tanks, lagoons, pits, waste piles, fresh
spills, or areas previously identified as contammated,
and require special handling procedures because of
their potential toxicity or hazard These samples can
be further subdivided based on their degree of hazard,
however, care should be taken when handling and
shipping any wastes believed to be concentrated
regardless of the degree
The importance of making the distinction between
environmental and hazardous samples is two-fold
(I) Personnel safety requirements Any sample
thought to contain enough hazardous
materials to pose a safety threat should be
designated as hazardous and handled in a
manner which ensures the safet)’ of both field
-and laboratoty personnel
(2) Transportation requirements Hazardous
samples must be packaged, labeled, and
shipped according to the International Air
Transport Association (JATA) Dangerous
Goods Regulations or Department of
Transportation (DOT) regulations and U S
EPA guidelines
7.2 Sam pie Collection Techniques
In general, two basic types of sample collection
techniques are recognized, both of which can be used
for either environmental or hazardous samples
Grab Samples
A grab sample is defined as a discrete aliquot
representative of a specrfic location at a given point in
time The sample is collected all at once at one
particular point in the sample medium The
representativeness of such samples is defined by the
nature of the materials being sampled In general, as
sources vaiy over time and distance, the
representativeness of grab samples will decrease
Composite Samples
Composites are nondiscrete samples composed of
more than one specific aliquot collected at various
sampling locations and/or different points in time
Analysis of this type of sample produces an average
value and can in certain instances be used as an
alternative to analyzing a number of individual grab
samples and calculating an average value It should
be noted, however, that compositing can mask
problems by diluting isolated concentrations of some
hazardous compounds below detection limits
Componting is often used for environmental samples
and may be used for hazardous samples under certain
conditions For example, compositing of hazardous
waste is often performed alter compatibility tests have
2
-------
been completed to determine an average value over a
number of different locations (group of drums) This
procedure generates data that can be useful by
providing an average concentration within a number
of units, can serve to keep analytical costs down, and
can provide information useful to transporters and
waste disposal operations
For sampling situations involving hazardous wastes,
grab sampling techniques are generally preferred
because grab sampling minimizes the amount of time
sampling personnel must be in contact with the
wastes, reduces risks associated with compositing
unknowns, and eliminates chemical changes that
might occur due to compositing
7.3 Types of Sampling Strategies
The number of samples that should be collected and
analyzed depends on the objective of the investigation
There are three basic sampling strategies random,
systematic, and judgmental sampling
Random sampling involves collection of samples in a
nonsystematic fashion from the entire site or a specific
portion of a site Systematic sampling involves
collection of samples based on a gnd or a pattern
which has been previously established When
judgmental sampling is performed, samples are
collected only from the portion(s) of the site most
likely to be contaminated Often, a combination of
these strategies is the best approach depending on the
type of the suspected/known contamination, the
uniformity and size of the site, the levelltype of
information desired, etc
7.4 QA Work Plans (QAWP)
A QAWP is required when it becomes evident that a
field investigation is necessary It should be initiated
in conjunction with, or immediately following,
notification of the field investigation This plan should
be clear and concise and should detail the following
basic components, with regard to sampling activities
C Objective and purpose of the investigation
C Basis upon which data will be evaluated
C information known about the site including
location, type and size of the facility, and
length of operations/abandonment
C Type and volume of contaminated material,
contaminants of concern (including
concentration), and basis of the
information/data
C Technical approach including media/matrix
to be sampled, sampling equipment to be
used, sample equipment decontamination (if
necessary), sampling design and rationale,
and SOPs or description of the procedure to
be implemented
C Pmject management and reporting, schedule,
project organization and responsibilities,
manpower and coal projections, and required
deliverables
C QA objectives arid protocols including tables
summarizing field sampling and QA/QC
analysis and objectives
Note that this list of QAWP components is not all-
inclusive and that additional elements may be added
or altered depending on the specific requirements of
the field investigation It should also be recognized
that although a detailed QAWP is quite important, it
may be impractical in some instances Emergency
responses and accidental spills are prime e>amples of
such instances where time might prohibit the
development of site-specific QAWPs prior to field
activities In such cases, investigators would have to
rely on general guidelines and personal judgment, and
the sampling oi response plans might simply be a
strategy based on preliminary information and
finalized on site In any event, a plan of action should
be developed, no matter how concise or informal, to
aid investigators in maintaining a logical and
consistent order to the implementation of their task
7.5 Legal Implications
The data derived from sampling activities are often
introduced as critical evidence during litigation of a
hazardous waste site cleanup Legal issues in which
sampling data are important may include cleanup cost
recovery, identification of pollution sources and
responsible parties, and technical vahdation of
remedial design methodologies Because of the
potential for involvement in legal actions, strict
adherence to technical and administrative SOPs is
essential during both the development and
implementation of sampling activities
Technically valid sampling begins with thorough
planning and continues through the sample collection
and analytical procedures Administrative
requirements involve thorough, accurate
3
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documentation of all sampling activittes 10.0 DATA VALIDATION
Documentation requirements include maintenance of
achain of custody, as well as accurate records of field Refer to the specific SOPs for data validation
activities and analytical instructions Failure to activities that are associated with sampling
observe these procedures fully and consistently may techniques
result in data that are questionable, invalid and
non-defensible in court, and the consequent loss of 11.0 HEALTH AND SAFETY
enforcement proceedings
When working with potentially hazardous materials,
8.0 CALCULATIONS follow U.S EPA, OSHA, and corporate health and
safety procedures
Refer to the specific SOPs for any calculations which
are associated with sampling techniques
9.0 QUALITY ASSURANCE/
QUALITY CONTROL
Refer to the specthc SOPs for the type and frequency
of QA/QC samples to be analyzed, the acceptance
cntena for the QAJQC samples, and any other QA/QC
activities which are associated with sampling
techniques
4
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SAMPLING EQUIPMENT
DECONTAMINATION
SOP#: 200L
DATE 08/11/94
REV. #. 0.0
1.0 SCOPE AND APPLICATION
The purpose of this Standard Operating Procedure
(SOP) is to provide a description of the methods used
for preventing, minimizing, or limiting
cross-contamination of samples due to inappropriate
or inadequate equipment decontamination and to
provide general , guidelines for developing
decontamination piocedures for sampling equipment
to be used dunng hazardous waste operations as per
29 Code of Federal Regulations (CFR) 1910 120
This SOP does not address personnel
decontamination
These are standard (i e typically applicable) operating
procedures which may be varied or changed as
required, dependent upon site conditions, equipment
limitation, or limitations imposed by the procedure
In all instances, the ultimate procedures employed
should be documented and associated with the final
report
Mention of trade names or commercial products does
not constitute U S Environmental Protection Agency
(U S EPA) endorsement or recommendation for use
2.0 METHOD SUMMARY
Removing or neutralizing contaminants from
equipment minimizes the likelihood of sample cross
contamination, reduces or eliminates transfer of
contaminants to clean areas, and prevents the mixing
of incompatible substances
Gross contamination can be removed by physical
decontamination procedures These abrasive and
non-abrasive methods include the use of brushes, air
and wet blasting, and high and low pressure water
cleaning
The first step, a soap and water wash, removes all
visible particulate matter and residual oils and grease
This may be preceded by a steam or high pressure
water wash to’facilitate residuals removal The
second step involves a tap water rinse and a
distilled/deionized water nnse to remove the
detergent An acid rinse provides a low pH media for
trace metals removal and is included in the
decontamination process if metal samples are to be
collected It is followed by another distilled/deionized
water rinse If sample analysis does not include
metals, the acid rinse step can be omitted Next, a
high purity solvent rinse is performed for trace
organics removal if organics are a concern at the site
Typical solvents used for removal of organic
contaminants include acetone, hexane, or water
Acetone is typically chosen because it is an excellent
solvent, miscible in water, and not a target analyte on
the Priority Pollutant List If acetone is known to be
a contaminant of concern at a given site or if Target
Compound List analysis (which includes acetone) is
to be performed, another solvent may be substituted
The solvent must be allowed to evaporate completely
and then a final distilled/deionized water rinse is
performed This rinse removes any residual traces of
the solvent
The decontamination procedure described above may
be summarized as follows
Physical removal
2 Non-phosphate detergent wash
3 Tap water nnse
4 Distilled/deionized water rinse
5 10% nitric acid nnse
6 Distilled/deionized water rinse
7 Solvent rinse (pesticide grade)
8 Airdry
9 Distilled/deionized water rinse
If a particular contaminant fraction is not present at
the site, the nine (9) step decontamination procedure
specified above may be modified for site specificity
For example, the nitric acid rinse may be eliminated
if metals are not of concern at a site Similarly, the
solvent rinse may be eliminated if organics are not of
1
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concern at a site Modifications to the standard
procedure should be documented in the site specific
work plan or subsequent report
3.0 SAMPLE PRESERVATION,
CONTAINERS, HANDLING,
AND STORAGE
The amount of sample to be collected and the proper
sample container type (i e , glass, plastic), chemical
preservation, and storage requirements are dependent
on the matrix being sampled and the parameter(s) of
interest
More specifically, sample collection and analysis of
decontamination waste may be required before
beginning proper disposal of decontamination liquids
and solids generated at a site This should be
determined prior to initiation of site activities
4.0 INTERFERENCES
POTENTIAL PROBLEMS
AND
C The use of distilled/deionized water
commonly available from commercial
vendors may be acceptable for
decontamination of sampling equipment
provided that it has been verifLed by
laboratoiy analysis to be analyte free
(specifically for the contaminants of
concern)
C The use of an untreated potable water supply
is not an acceptable substitute for tap water
Tap water may be used from any municipal
or industrial water treatment system
C If acids or solvents are utilized in
decontamination they raise health and safety,
and waste disposal concerns
C Damage can be incurred by acid and solvent
washing of complex and sophisticated
sampling equipment
5.0 EQUIPMENT/APPARATUS
Decontamination equipment, materials, and supplies
are generally selected based on availability Other
considerations include the ease of decontaminating or
disposing of the equipment Most equipment and
supplies can be easily procured For example, soft-
bristle scrub brushes or long-handled bottle brushes
can be used to remove contaminants Large
galvanized wash tubs, stock tanks, or buckets can hold
wash and rinse solutions Children’s wading pools can
also be used Large plastic garbage cans or other
similar containers lined with plastic bags can help
segregate contaminated equipment Contaminated
liquid can be stored temporanly in metal or plastic
cans or
-------
general, the following solvents are typically utilized
for decontamination purposes
C 10% nitnc acid is typically used for
inorganic compounds such as metals An
acid rinse may not be required if inorganics
are not a contaminant of concern
C Acetone (pesticide grade)°
C Hexane (pesticide grade)°
C Methano1°
- Only if sample is to be analyzed for organics
7.0 PROCEDURES
As part of the health and safety plan, a
decontamination plan should be developed and
reviewed The decontamination line should be set up
before any personnel or equipment enter the areas of
potential exposure The equipment decontamination
plan should include
C The number, location, and layout of
decontamination stations
C Decontamination equipment needed
C Appropnate decontamination methods
C Methods for disposal of contaminated
clothmg, equipment, and solutions
C Procedures can be established to minimize
the potential for contamination This may
include (I) work practices that minimize
contact with potential contaminants, (2)
using remote sampling techniques, (3)
covenng momtonng and sampling equipment
with plastic, aluminum foil, or other
protective material, (4) watering down dusty
areas, (5) avoiding laying down equipment in
areas of obvious contamination, and (6) use
of disposable sampling equipment
7.1 Decontamination Methods
All samples and equipment leaving the contaminated
area of a site must be decontaminated to remove any
contamination that may have adhered to equipment
Various decontamination methods will remove
contaminants by (1) flushing or other physical
action, or (2) chemical complexing to inactivate
contaminants by neutralization, chemical reaction,
disinfection, or sterilization
Physical decontamination techniques can be grouped
into two categories abrasive methods and
non-abrasive methods, as follows
7 11 Abrasive Cleaning Methods
Abrasive cleaning methods work by rubbing and
wearing away the top layer of the surface containing
the contaminant The mechanical abrasive cleaning
methods are most commonly used at hazardous waste
sites The following abrasive methods are available
Mechanical
Mechanical methods of decontamination include using
metal or nylon brushes The amount and type of
contaminants removed will vary with the hardness of
bristles, length of time brushed, degree of brush
contact, degree of contamination, nature of the surface
being cleaned, and degree of contaminant adherence
to the surface
Air Blasting
Air blasting equipment uses compressed air to force
abrasive material through a nozzle at high velocities
The distance between nozzle and surface cleaned, air
pressure, time of application, and angle at which the
abrasive strikes the surface will dictate cleaning
efficiency Disadvantages of this method are the
inability to control the amount of material removed
and the large amount of waste generated
Wet Blasting
Wet blast cleaning involves use of a suspended fine
abrasive The abrasive/water mixture is delivered by
compressed air to the contaminated area By using a
very fine abrasive, the amount of materials removed
can be carefully controlled
7 1 2 Non-Abrasive Cleaning Methods
Non-abrasive cleaning methods work by forcing the
contaminant off a surface with pressure In general,
the equipment surface is not removed using
non-abrasive methods
3
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Low-Pressure Water
This method consists of a container which is filled
with water The user pumps air out of the container to
create a vacuum A slender nozzle and hose allow the
user to spray in hard-to-reach places
High-Pressure Water
This method consists of a high-pressure pump, an
operator controlled directional nozzle, and a high-
pressure hose Operating pressure usually ranges
from 340 to 680 atmospheres (atm) and flow rates
usually range from 20 to 140 liters per minute
Ultra-i-ugh-Pressure Water
This system produces a water jet that is pressured
from 1,000 to 4,000 atmospheres This
ultra-high-pressure spray can remove tightly-adhered
surface films The water velocity ranges from 500
meters/second (mIs) (1,000 atm) to 900 m/s (4,000
atm) Additives can be used to enhance the cleaning
action
Rinsing
Contaminants are removed by rinsing through
dilution, physical attraction, and solubilization
Damp Cloth Removal
In some instances, due to sensitive, non-waterproof
equipment or due to the unltkelthocd of equipment
being contaminated, it is not necessary to conduct an
extensive decontamination procedure For example,
air sampling pumps hooked on a fence, placed on a
drum, or wrapped in plastic bags are not likely to
become heavily contaminated A damp cloth should
be used to wipe off contaminants which may have
adhered to equipment through airborne contaminants
or from surfaces upon which the equipment was set
Distnfectiori/Sterijization
Disinfectants are a practical means of inactivating
infectious agents Unfortunately, standard
sterilization methods are impractical for large
equipment This method of decontamination is
typically performed off-site
7.1 Field Sampling Equipment
Decontamination Procedures
The decontamination line is setup so that the first
station is used to clean the most contaminated item
It progresses to the last station where the least
contaminated item is cleaned The spread of
contaminants is further reduced by separating each
decontamination station by a minimum of three (3)
feet Ideally, the contamination should decrease as the
equipment progresses from one station to another
farther along in the line
A site is typically divided up into the following
boundaries I-lot Zone or Exclusion Zone (EZ), the
Contamination Reduction Zone (CRZ), and the
Support or Safe Zone (SZ) The decontamination line
should be setup in the Contamination Reduction
Comdor (CRC) which is in the CRZ Figure 1
(Appendix B) shows a typical contaminant reduction
zone layout The CRC controls access into and out of
the exclusion zone and confines decontamination
activities to a limited area The CRC boundanes
should be conspicuously marked The far end is the
hothne, the boundary between the exclusion zone and
the contamination reduction zone The size of the
decontamination corridor depends on the number of
stations in the decontamination process, overall
dimensions of the work zones, and amount of space
available at the site Whenever possible, it should be
a straight line
Anyone in the CRC should be wearing the level of
protection designated for the decontamination crew
Another comdor may be required for the entry and
exit of heavy equipment Sampling and monitoring
equipment and sampling supplies are all maintained
outside of the CRC Personnel don their equipment
away from the CRC and enter the exclusion zone
thmugh a separate access control point at the hotime
One person (or more) dedicated to decontaminating
equipment is recommended
7.2 1 Decontamination Setup
Starting with the most contaminated station, the
decontamination setup should be as follows
Station I Segregate Eciuipment Drop
Place plastic sheeting on the ground (Figure 2,
Appendix B) Size will depend on amount of
4
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equipment to be decontaminated Provide containers
lined with plastic if equipment is to be segregated
Segregation may be required if sensitive equipment or
mildly contaminated equipment is used at the same
time as equipment which is likely to be heavily
contaminated
Station 2 Physical Removal With A High-Pressure
Washer (Optional )
As indicated in 7 1 2, a high-pressure wash may be
required for compounds which are difficult to remove
by washing with brushes The elevated temperature of
the water from the high-pressure washers is excellent
at removing greasy/oily compounds High pressure
washers require water and electricity
poo 1 with tap water Several bottle and bnstle brushes
should be dedicated to this station Approximately
10-50 gallons of water may be required initially
depending upon the amount of equipment to
decontaminate and the amount of gross contamination
Station 5 Low-Pressure Sprayers
- Fill a low-pressure-sprayer with distilled/deionized
water Provide a 5-gallon bucket or basin to contain
the water during the rinsing process Approximately
10-20 gallons of water may be required initially
depending upon the amount of equipment to
decontaminate and the amount of gross contamination
Station 6 Nitric Acid Sprayers
A decontamination pad may be required for the high-
pressure wash area An example of a wash pad may
consist of an approximately 1 1/2 foot-deep basin
lined with plastic sheeting and sloped to a sump at one
corner A layer of sand can be placed over the plastic
and the basin is filled with gravel or shell The sump
is also lined with visqueen and a barrel is placed in the
hole to prevent collapse A sump pump is used to
remove the water from the sump for transfer into a
drum
Typically heavy machinery is decontaminated at the
end of the day unless site sampling requires that the
machinery be decontaminated frequently A separate
decontamination pad may be required for heavy
equipment
Station 3 Physical Removal With Brushes And A
Wash Basin
Prior to setting up Station 3, place plastic sheeting on
the ground to cover areas under Station 3 through
Station 10
Fill a wash basin, a large bucket, or child’s swimming
pool with non-phosphate detergent and tap water
Several bottle and bnstle brushes to physically remove
contamination should be dedicated to this station
Approximately 10 - 50 gallons of water may be
required initially depending upon the amount of
equipment to decontaminate and the amount of gross
contamination
Fill a spray bottle with 10% nitric acid An acid rinse
may not be required if inorganics are not a
contaminant of concern The amount of acid will
depend on the amount of equipment to be
decontaminated Provide a 5-gallon bucket or basin to
collect acid during the rinsing process
Station 7 Low-Pressure Sprayers
Fill a low-pressure sprayer with distilled/deionized
water Provide a 5-gallon bucket or basin to collect
water during the rinsate process
Station 8 Organic Solvent Sprayers
Fill a spray bottle with an organic solvent Alter each
solvent rinse, the equipment should be rinsed with
distilled/deionized waler and air dried Amount of
solvent will depend on the amount of equipment to
decontaminate Provide a 5-gallon bucket or basin to
collect the solvent during the rinsing process
Solvent rinses may not be required unless organics are
a contaminant of concern, and may be eliminated from
the station sequence
Station 9 Low-Pressure Sprayers
Fill a low-pressure sprayer with distilled/deionized
water Provide a 5-gallon bucket or basin to collect
water during the rinsate process
Station 4 Water Basin
Station 10 Clean Equipment Drop
Fill a wash basin, a large bucket, or child’s swimming
Lay a clean piece of plastic sheeting over the bottom
5
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plastic layer This will allow easy removal of the
plastic in the event that it becomes dirty Provide
aluminum foil, plastic, or other protective material to
wrap clean equipment
7.2 2 Decontamination Procedures
Station I Segregate Equipment Drop
Deposit equipment used on-site (i e , tools, sampling
devices and containers, monitoring instruments radios,
clipboards, etc) on the plastic drop cloth/sheet or in
different containers with plastic liners Each will be
contaminated to a different degree Segregation at the
drop reduces the probability of cross contamination
Loose leaf sampling data sheets or maps can be placed
in plastic zip lock bags if contamination is evident
Station 2 Physical Removal With A High-Pressure
Washer (Optional )
Use high pressure wash on grossly contaminated
equipment Do not use high- pressure wash on
sensitive or non-waterproof equipment
Station 3 Physical Removal With Brushes And A
Wash Basin
Using a spray bottle rinse sampling equipment with
nitric acid Begin spraying (inside and outside) at one
end of the equipment allowing the acid to drip to the
other end into a 5-gallon bucket A nnsate blank may
be required at this station Refer to Section 9
Station 7 Low-Pressure Sprayers
Rinse sampling equipment with distilled/deionized
water with a low-pressure sprayer
Station 8 Organic So’vent Sprayers
Rinse sampling equipment with a solvent Begin
spraying (inside and outside) at one end of the
equipment allowing the solvent to drip to the other
end into a 5-gallon bucket Allow the solvent to
evaporate from the equipment before going to the next
station A QC rinsate sample may be required at this
station
Station 9 Low-Pressure Sprayers
Rinse sampling equipment with distilled/deionized
water with a low-pressure washer
Station 10 Clean Equipment Drop
Scrub equipment with soap and water using bottle and
bristle brushes Only sensitive equipment (i e , radios,
air monitoring and sampling equipment) which is
waterproof should be washed Equipment which is
not waterproof should have plastic bags removed and
wiped down with a damp cloth Acids and organic
rinses may also rum sensitive equipment Consult the
manufacturers for recommended decontamination
solutions
Station 4 Equipment Rinse
Wash soap off of equipment with water by immersing
the equipment in the water while brushing Repeat as
many times as necessary
Station S Low-Pressure Rinse
Rinse sampling equipment with distilled/deionized
water with a low-pressure sprayer
Station 6 Nitnc Acid Sprayers ( required only if
metals are a contaminant of concern )
Lay clean equipment on plastic sheeting Once air
dried, wrap sampling equipment with aluminum foil,
plastic, or other protective material
7 2 3 Post Decontamination Procedures
Collect high-pressure pad and heavy
equipment decontamination area liquid and
waste and store in appropriate drum or
container A sump pump can aid in the
collection process Refer to the Department
of Transportation (DOT) requirements for
appropriate containers based on the
contaminant of concern
2 Collect high-pressure pad and heavy
equipment decontamination area solid waste
and store in appropriate drum or container
Refer to the DOT requirements for
appropriate containers based on the
contaminant of concern
3 Empty soap and water liquid wastes from
basins and buckets and store in appropriate
6
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drum or container Refer to the DOT
requirements for appropriate containers
based on the contaminant of concern
4 Empty acid nnse waste and place in
appropnate container or neutralize with a
base and place in appropriate drum pH
paper or an equivalent pH test is required for
neutralization Consult DOT requirements
for appropriate drum for acid rinse waste
5 Empty solvent nnse sprayer and solvent
waste into an appropnate container Consult
DOT requirements for appropriate drum for
solvent rinse waste
6 Using low-pressure sprayers, rinse basins,
and brushes Place liquid generated from
this process into the wash water rinse
container
7 Empty low-pressure sprayer water onto the
ground
8 Place all solid waste matenals generated
from the decontamination area (i e, gloves
and plastic sheeting, etc) in an approved
DOT drum Refer to the DOT requirements
for appropriate containers based on the
contaminant of concern
9 Wnte appropnate labels for waste and make
arrangements for disposal Consult DOT
regulations for the appropnate label for each
drum generated from the decontamination
process
8.0 CALCULATIONS
This section is not applicable to this SOP
9.0 QUALITYASSURANCE/
QUALITY CONTROL
A rmsate blank is one specific type of quality conirol
sample associated with the field decontamination
process This sample will provide information on the
effectiveness of the decontamination process
employed in the field
Rinsate blanks are samples obtained by running
analyte free water over decontaminated sampling
equipment to test for residual contamination The
blank water is collected in sample containers for
handling, shipment, and analysis These samples are
treated identical to samples collected that day A
rinsate blank is used to assess cross contamination
brought about by improper decontamination
procedures Where dedicated sampling equipment is
not utilized, collect one nnsate blank per day per type
of sampling device samples to meet QA2 and QA3
objectives
If sampling equipment requires the use of plastic
tubing it should be disposed of as contaminated and
replaced with clean tubing before additional sampling
occurs
10.0 DATA VALIDATION
Results of quality control samples will be evaluated
for contamination This information will be utilized
to qualify the environmental sample results in
accordance with the project’s data quality objectives
11.0 HEALTH AND SAFETY
When working with potentially hazardous materials,
follow OSHA, U.S EPA, corporate, and other
applicable health and safety procedures
Decontamination can pose hazards under certain
circumstances Hazardous substances may be
incompatible with decontamination materials For
example, the decontamination solution may react with
contaminants to produce heat, explosion, or toxic
products Also, vapors from decontamination
solutions may pose a direct health hazard to workers
by inhalation, contact, fire, or explosion
The decontamination solutions must be determined to
be acceptable before use Decontamination materials
may degrade protective clothing or equipment, some
solvents can permeate protective clothing If
decontamination materials do pose a health hazard,
measures should be taken to protect personnel or
substitutions should be made to eliminate the hazard
The choice of respiratory protection based on
contaminants of concern from the site may not be
appropriate for solvents used in the decontamination
process
Safety considerations should be addressed when using
abrasive and non-abrasive decontamination
7
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equipment Maximum air pressure produced by 12.0 REFERENCES
abrasive equipment could cause physical injury
Displaced material requires control mechanisms Field Sampling Procedures Manual, New Jersey
Department of Environmental Protection, February,
Material generated from decontamination activities 1988
requires proper handling, storage, and disposal
Personal Protective Equipment may be required for A Compendium of Superfund Field Operations
these activities Methods, EPA 54O/p-W7/OOI
Material safety data sheets are required for all Engineenng Support Branch Standard Operating
decontamination solvents or solutions as required by Procedures and Quality Assurance Manual, USEPA
the Hazard Communication Standard (i e, acetone, Region IV, April 1, 1986
alcohol, and tnsodiumphosphate)
Guidelines for the Selection of Chemical Protective
In some jurisdictions, phosphate containing detergents Clothing, Volume 1, Third Edition, American
(i e , TSP) are banned Conference of Governmental Industrial Hygienists.
Inc,Februaiy, 1987
Occupational Safety and Health Guidance Manual for
Hazardous Waste Site Activities,
NIOSHIOSHAIUSCGIEPA, October, 1985
8
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APPENDIX A
Table
Table I Soluble Contaminants and Recommended Solvent Rins
TABLE 1
Soluble Contaminants and Recommended Solvent Rinse
SOLVENT°
EXAMPLES OF
SOLVENTS
SOLUBLE
CONTAMINANTS
Water
Deionized water
Tap water
Low-chain hydrocarbons
Inorganic compounds
Salts
Some organic acids and other polar
compounds
Dilute Acids
Nitric acid
Acetic acid
Boric acid
Basic (caustic) compounds (e g., amines
and hydrazines)
Dilute Bases
Sodium bicarbonate (e g,
soap detergent)
Acidic compounds
Phenol
Thiols
Some nitro and sulfonic compounds
Organic Solvents (2)
Alcohols
Ethers
Ketones
Aromatics
Straight chain alkalines
(e.g.,
hexane)
Common petroleum
products (e.g, fuel, oil,
kerosene)
Nonpolar compounds (e g, some
organic compounds)
Organic SoIvent 2
Hexane
PCBs
(i) - Material safety data sheets are required for all decontamination solvents or solutions as require
by the Hazard Communication Standard
(2) - WARNING Some organic solvents can permeate andlor degrade the protective clothing
9
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APPENDIX B
Figures
Figure 1 Contamination Reduction Zone Layout
NLAYY CDVIWD(T
EW ‘ W
C— C
LFCENfl
-HOTLINE
CONTAMINATION CONTROL UNE
.i ACCtSS CONTROL POINT—ENTRANCE
::: *ccrss CONTROL POINT—EXIT
PATh
10
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APPENDIX B (Cont’d.)
Figures
Figure 2 Decontamination Layout
HEAVY LOUWUCWI
DECOWTAWIMATION
—D
ZCPE
StGflOAVID
£OLIPMENT D1OP
C
WASH IASIN WITH SOAP
£140 TAP WATU
x
—u
x
0
U
RINSE RASIN WITH TAP WATEI
LOW P* SUE SPRAYER
WITH DIS11LLED WATER
NITRIC ACID SPRAYER
(MAY ND! u REOUIRED)
LOW PlESSU t SPRAYER
WITH DISTiLLED WAILI
(MAY NOT SE REOUtRED)
O GAI41C SOLVENT SPRAYER
(MAY NOT SE REOUIRED)
LOW PIESSUIC SPRAYER
WITH DlSTU.LED WATER
NOT It REQUIRED)
CLEAN COUIPMENT DROP
LZCfN.D
HOTLINt
‘CONTAMINATION CONTROL UNE
PLSTIC SHEETING
OVERLAPPING PLASTIC SHEETING
PATH
L...
11
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WATER LEVEL
MEASUREMENT
SOP 204.
DATE 10/03/94
REV #. 0.0
1.0 SCOPE AND APPLICATION
The purpose of this Standard Operating Procedure
(SOP) is to set guidelines for the determmation of the
depth to water and floating chemical product (i e,
gasoline, kerosene) in an open borehole, cased
borehole, monitoring well or piezometer
Generally, water level measurements taken in
boreholes, piezometers, or monitoring wells are used
to construct water table or potentiometric surface
maps and to determine flow direction as well as many
other aquifer characteristics Therefore, alt water
level measurements at a given site should be collected
within a 24-hour period with a great deal of accuracy
Certain situations may necessitate that all water level
measurements be taken within a shorter time interval
These situations may include
The magnitude of the observed changes
between wells appears too large
2 Atmospheric pressure changes
3 Aquifers which are tidally influenced
4 Aquifers affected by river stage,
impoundments, and/or unlined ditches
5 Aquifers stressed by mtermittent pumping of
production wells
6 Aquifers being actively recharged due to
precipitation event
7 Occurrence of pumping
These are standard (1 e., typically applicable)
operating procedures which may be varied or changed
as required, dependent on site conditions, equipment
limitations or limitations imposed by the procedure or
other procedure limitations In all instances, the
ultimate procedures employed should be documented
and associated with the final report
Mention of trade names or commercial products does
not constitute U S EPA endorsement or
recommendation for use
2.0 METHOD SUMMARY
A survey mark should be placed on the casing for use
as a reference point for measurement Generally, the
reference point is made at the top of casing or
“stickup,” but often the lip of the riser pipe is not flat
Another measuring reference should be located on the
grout apron The measuring point should be
documented in the site logbook and on the
groundwater level data form (Appendix A) Every
attempt should be made to notify future field
personnel of such reference point in order to ensure
comparable data and measurements
Pnor to measurement, water levels in piezometers and
monitoring wells should be allowed to stabilize for a
minimum of 24 hours after well construction and
development In low yield situations, recovery may
take longer All measurements should be made to an
accuracy of 0 01 feet
In general, working with decontaminated equipment,
proceed from least to most contaminated wells
Where many wells are to be sampled (i e., greater than
ten), measurements may be taken in a systematic
manner to insure efficiency and accuracy Open the
well and monitor headspace with the appropriate
monitoring instrument to determine the presence of
volatile organic compounds Lower water level
measurement device into well until water surface or
bottom of casing at least twice is encountered
Measure distance from water surface to reference
point on well casing at least twice and record in site
logbook and/or groundwater level data form Remove
all downhole equipment, decontaminate as necessary,
and replace casing cap Note that if floating
hydrocarbon product is present, a special dual liquid
water level indicator is required
-------
3.0 SAMPLE PRESERVATION,
CONTAINERS, HANDLING AND
STORAGE
This section is not applicable to this standard
operating procedure (SOP)
4.0 INTERFERENCES
POTENTIAL PROBLEMS
AND
The chalk used on steel tape may
contaminate the well
2 Cascading water may obscure the water mark
or cause it to be inaccurate
3 Many types of electnc sounders use metal
indicators at five-foot intervals around a
conducting wire These intervals should be
checked with a surveyor’s tape (preferably
with units divided in hundredths of a foot) to
insure accuracy
4 If there is oil present on the water, it can
insulate the contacts of the probe on an
electric sounder or give false readings due to
thickness of the oil It is recommended to
determine the thickness and density of the oil
layer in order to determine the correct water
level A special liquid water level indicator
is required
S Turbulence in the well andlor cascading
water can make water level determination
difficult with either an electnc sounder or
steel tape
6 An airline measures drawdown dunng
pumping It is only accurate to 0 5 foot
unless it is calibrated for various drawd owns
5.0 EQUIPMENT/APPARATUS
There are a number of devices which can be used to
measure water levels The device must be capable of
attaining an accuracy of 0 01 feet, and calibrated on a
regular basis
Field equipment includes
C Air monitoring equipment
C Well depth measurement device
C Electronic water level indicator
C Metal tape measure
C Airline
C Chalk
C Ruler
C Logbook
C Paper towels
C Groundwater water level data forms
C pH meter (optional)
C Specific conductivity meter (optional)
C Thermometer (optional)
6.0 REAGENTS
No chemical reagents are used in this procedure,
however, decontamination solutions may be
necessary If decontamination of equipment is
required, refer to the SOP for Sampling Equipment
Decontamination, and the site specific work plan
7.0 PROCEDURES
7.1 Preparation
Determine the extent of the sampling effort,
the sampling methods to be employed, and
the types and amounts of equipment and
supplies needed
2 Obtain necessary sampling and monitonng
equipment
3 Decontaminate or pre-clean equipment, and
ensure that it is in working order
4 Prepare scheduling and coordinate with staff,
clients, and regulatory agency, if appropriate
5 Perform a general site survey prior to site
entry in accordance with the site specific
Health and Safety Plan
6 Identify and mark all sampling locations
7.2 Procedures
Procedures for determining water levels are as
follows
Make sure water level measuring equipment
is in good operating condition
2
-------
2 If possible and when applicable, start at those
wells that are least contaminated and proceed
to those wells that are most contaminated
3 Clean all equipment entering well by the
following decontamination procedure
C Triple rinse equipment with
deionized water
C Wash equipment with an Alconox
solution which is followed by a
deionized water nnse
C Rinse with an approved solvent
(e g, methanol, isopropyl alcohol,
acetone) as per the work plan, if
c anic contamination is suspected
C Place equipment on clean surface
such as a teflon or polyethylene
sheet
4 Remove locking well cap, note well ID, time
of day, elevation (top of casing) and date in
site logbook or an appropriate groundwater
level data form
5 Remove well casing cap
6 If required by site-specific condition, monitor
headspace of well with a photoionization
detector (PID) or flame ionization detector
(FID) to determine presence of volatile
organic compounds, and record in site
logbook
7 Lower electric water level measuring device
or equivalent (i e, permanently installed
transducers or airline) into the well until
water surface is encountered
8 Measure the distance from the water surface
to the reference measuring point on the well
casing or protective barrier post and record in
the site logbook In addition, note that the
water level measurement was from the top of
the steel casing, the top of the PVC riser
pipe, the ground surface, or some other
position on the well head
9 The groundwater level data forms (Form I,
Appendix A) should be completed as
follows
C Site Name Site name
C Logger Name Person taking field
notes
C Date Date when the water levels
are being measured
C Location Monitor well number and
physical location
C Time Time (military time) at which
the water level measurement was
recorded
C Depth to Water Water level
measurement in feet, tenths, or
hundredths of feet, depending on the
equipment used Two
measurements arc required to insure
accuracy
C Comments Any information the
field personnel feels to be
applicable may be included here
C Measuring Point Marked
measuring point on PVC nser pipe,
protective steel casing or concrete
pad surrounding well casing from
which all water level measurements
for individual wells should be
measured This provides
consistency in future water level
measurements
10 Measure total depth of well (at least twice to
confirm measurement) and record in site
logbook or on groundwater level data form
II Remove all downhole equipment, replace
well casing cap and locking steel caps
12 Rinse all downhole equipment and store for
transport to next well Decontaminate all
equipment as outlined in Step 3 above
13 Note any physical changes, such as erosion
or cracks in protective concrete pad or
variation in total depth of well, in field
logbook and on groundwater level data form
3
-------
8.0 CALCULATIONS
To determine groundwater elevation above mean sea
level, use the following equation
where
E ’ E&D
E = Elevation of water above mean sea
level (ft) or local datum
E = Elevation above sea level or local
datum at point of measurement (ft)
D Depth to water (ft)
9.0 QUALITY ASSURANCE/
QUALITY CONTROL
The following general quality assurance
procedures apply
All data must be documented on standard
chain of custody forms, field data sheets,
groundwater level data forms, or within
personal/site logbooks
2 All instrumentation must be operated in
accordance with operating instructions as
supplied by the manufacturer, unless
otherwise specified in the work plan
Equipment checkout and calibration
activities must occur prior to
sampling/operation, and they must be
documented
3 Each well should be tested at least twice in
order to compare results
10.0 DATA VALIDATION
This section is not applicable to this SOP
11.0 HEALTH AND SAFETY
When working with potentially hazardous materials,
follow U S EPA, OSHA, or corporate health and
safety practices
12.0 REFERENCES
US Environmental Protection Agency, 1986 RCRA
Groundwater Monitoring Technical Enforcement
Guidance Document, pp 207
U S Environmental Protection Agency, 1987, A
Compendium of Superfund Field Operations Methods
EPAI54O/p-87/O0l Office of Emergency and
Remedial Response Washington, D C 20460
4
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APPENDIX A
Groundwater Level Data Form
FORM I Groundwater Level Data Form
PAGE OF
SITE NAME ________________________ LOGGER NAME - _______
LOGDATE ___________________ WA#
Well I.D
TIME
Well
Depth to
Depth to
COMMENTS
Elevation
Bottom of
Water (ft)
(pH, temperature,
(T 0 C)
Well (ft)
specific conductance)
MEASUREMEN’l’ REFERENCE POINT FROM — TOP OF GROUND OR — TOP OF CASING
Weather Conditions
Other significant observations
5
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WELL DEVELOPMENT
SOP1 204
DATE 10/03/94
REV #. 0.0
1.0 SCOPE AND APPLICATION
The purpose of this standard operating procedure
(SOP) is to provide an overview of monitor well
development practices The purpose of monitor well
development is to ensure removal of fines from the
vicinity of the well screen This allows free flow of
water from the formation into the well and also
reduces the turbidity of the water during sampling
events The most common well development methods
are surging, jetting, overpumping and bailing
Surging involves raising and lowering a surge block or
surge plunger inside the well The resulting surging
motion forces water into the formation and loosens
sediment to be pulled from the formation into the
well Occasionally, sediments must be removed from
the well with a sand bailer to prevent sand locking of
the surge block This method may cause the sand
pack amund the screen to be displaced to a degree that
damages its value as a filtering medium For
example, channels or voids may form near the screen
if the filter pack sloughs away dunng surging (Keely
and Boateng, 1987)
Jetting involves lowering a small diameter pipe into
the well a few feet above the well screen and
injecting water or air through the pipe under pressure
so that sediments at the bottom are geysered out of the
top of the well It is important not to jet air or water
directly across the screen This may cause fines in the
well to be driven into the entrance of the screen
openings, thereby causing blockages
Overpumping involves pumping at a rate rapid enough
to draw the water level in the well as low as possible,
and allowing it to recharge This process is repeated
until sediment-free water is produced
Bailing includes using a simple check-valve bailer to
remove water from the well The bailing method, like
other methods, should be repeated until sediment free
water is produced Bailing may be the method of
choice in a shallow well or well that recharges slowly
These are standard (i e , typically applicable)
operating procedures which may be varied or changed
as required, dependent on site conditions, equipment
limitations or limitations imposed by the procedure or
other procedure limitations In all instances, the
ultimate procedures employed should be documented
and associated with the final report
Mention of trade names or commercial products does
not constitute U S EPA endorsement or
recommendation for use
2.0 METHOD SUMMARY
Development of a well should occur as soon as it is
practical after installation, but not sooner than 48
hours after grouting is completed, if a rigorous well
development method is being used If a less rigorous
method, such as bailing, is used for development, it
may be initiated shortly after installation The main
concern is that the method being used for development
does not interfere with allowing the grout to set
Open the monitoring well, take initial measurements
(i e , head space air monitor readings, water level,
well depth, pH, temperature, and specific
conductivity) and record results in the site logbook
Develop the well by the appropriate method (i e,
overpumping, jetting, or surging) to accommodate site
conditions and project requirements Continue until
the developed water is clear and free of sediments
Containerize all discharge water from known or
suspected contaminated areas Record final
measurements in logbook Decontaminate equipment
as appropriate prior to use in the next well
3.0 SAMPLE PRESERVATION,
CONTAINERS, HANDLING,
AND STORAGE
This section is not applicable to this (SOP)
-------
4.0 INTERFERENCES
POTENTIAL PROBLEMS
AND
The following interferences or problems may occur
during well development
Overpumping is not as vigorous as surging
and jetting, and is probably the most
desirable method for monitor well
development
2 The possibility of disturbing the filter pack
increases with surging and jetting well
development methods
3 The introduction of external water or air by
jetting may alter the hydrochemistry of the
aquifer
5.0 EQUIPMENT/APPARATUS
The type of equipment used for well development is
dependent on the diameter of the well and the
development method For example, the diameter of
most submersible pumps is too large to fit in a two-
inch inner diameter (I D ) well and an inertia pump or
other development method should be used
In general, the well should be developed with the
drilling equipment shortly after it is drilled Most
drilling ngs have air compressors or pumps that may
be used for the development process
6.0 REAGENTS
No chemical reagents are used in this procedure,
however, decontamination solutions may be
necessary If decontamination of equipment is
required at a well, refer to the SOP for Sampling
Equipment Decontamination and the site specific
work plan
7.0 PROCEDURES
7.1 Preparation
Coordinate site access and obtain keys to the
locks
2 Obtain information on each well to be
developed (i e , drilling, method, well
diameter, depth, screened
anticipated contaminations, etc )
interval,
3 Obtain a water level meter, a depth sounder,
air monitoring equipment, materials for
decontamination, p1-I and specific
conductivity meters, a thermometer,
stopwatch, and development
-equipment/apparatus
4 Assemble containers for temporary storage
of water produced dunng well development
Containers must be structurally sound,
compatible with anticipated contaminants,
and easy to manage in the field The use of
truck-mounted tanks may be necessary in
some cases, alternately, a portable water
treatment unit (i e, activated carbon) may be
used to decontaminate the purge water
7.2 Operation
Development should be performed as soon as it is
practical after the well is installed, but no sooner than
48 hours after grouting is completed Dispersing
agents, acids, or disinfectants should not be used to
enhance development of the well
I Assemble necessary equipment on a plastic
sheet around the well
2 Record pertinent information in field logbook
(personnel, time, location ID, etc)
3 Open monitor well, take air monitoring
reading at the top of casing and breathing
zone as appropriate
4 Measure depth to water and the total depth of
the monitoring well
5 Develop the well until the water is clear and
free of sediments Note the initial color,
clarity, and odor of the water
6 Measure the initial pH, temperature, and
specific conductivity of the water and record
in logbook
7 All water produced by development in
contaminated or suspected contaminated
areas must be containenzed or treated Each
2
-------
container must be clearly labeled with the
location ID Determination of the
appropnate disposal method will be based on
the first round of analytical results from each
well
8 No water shall be added to the well to assist
development without prior approval by
appropnate personnel If a well cannot be
cleaned of mud to produce formation water
because the aquifer yields insufficient water,
small amounts of potable water may be
injected to clean up this poorly yielding well
This may be done by dumping in buckets of
water When most of the mud is out,
continue development with formation water
only It is essential that at least five times
the amount of water injected must be
produced back from the well in order to
assure that all injected water is removed
from the formation
9 Note the final color, clanty and odor of the
water
10 Measure the final pH, temperature and
specific conductance of the water and record
in the site logbook
II Record the following data in the site
logbook
C Well designation (location ID)
C Date(s) of well installation
C Date(s) and time of well
development
C Static water level before and after
development
C Quantity of water removed and time
of removal
C Type and size/capacity of pump
andIor bailer used
C Descnption of well development
techniques used
7.3 Post-Operation
Decontaminate all equipment
2 Store containers of water produced during
development in a safe and secure area
3 Afler the first round of analytical results have
been received, determine and implement the
appropriate water disposal method
8.0 CALCULATIONS
There are no calculations necessary to implement this
procedure However, if it is necessary to calculate the
volume of -water in the well, utilize the following
equation
Well volume • Br 2 h (cf) (Equaiion 11
where
B = pi
r = radius of monitoring well (feet)
h = height of the water column (feet)
[ This may be determined by
subtracting the depth to water from
the total depth of the well as
measured from the same reference
point]
cf = conversion factor (gal/ft 3 ) = 7 48
gal/ft 3 [ In this equation, 7 48 gal/ft 3
is the necessary conversion factor]
Monitorwell diameters are typically 2”, 3”, 4”, or 6”
Knowing the diameter of the monitor well, there are
a number of standard conversion factors which can be
used to simplify the equation above
The volume, in gallons per linear foot, for various
standard monitor well diameters can be calculated as
follows
where
B
r
cf
V (gal/fl) ‘ 2 (cf) IEqualion 2J
= pi
= radius of monitoring well (feet)
= conversion factor (7 48 gal/ft 3 )
For example, a two inch diameter well, the volume
per linear foot can be calculated as follows
vol/linear ft
nr 2 (ci) [ Equation 2]
= 3 l4(l/l2ft) 2 748 gal/ft 3
= 0 1632 gal/ft
3
-------
Remember that if you have a two inch diameter, well
you must convert this to the radius in feet to be able to
use the equation
The conversion factors for the common size monitor
wells are as follows
If you utilize the conversation factors above,
Equation I should be modified as foilows
Well volume ‘ (h)(cJ) [ Equation 3J
= h.ight of water column (feet)
= the conversion factor calculated
from Equation 2
9.0 QUALITY ASSURANCE!
QUALITY CONTROL
There are no specific quality assurance activities
which apply to the implementation of these
procedures However, the following general QA
procedures apply
All data must be documented in personal/site
logbooks
2 All instrumentation must be operated in
accordance with operating instructions as
supplied by the manufacturer, unless
otherwise specified in the work plan
Equipment checkout and calibration
activities must occur prior to
sampling/operation and they must be
documented
10.0 DATA VALIDATION
This section is not applicable to this SOP
11.0 HEALTH AND SAFETY
When working with potentially hazardous materials,
follow U S EPA, OSHA, and corporate health and
safety practices
12.0 REFERENCES
Driscoll, Fletcher 0 , Groundwater and Wells, 2nd
ed , Johnson Division, VOP Inc. St Paul, Minnesota,
l986,p 1089
Freeze, Allan R and John A Cherry, Groundwater,
Prentice-Hall, Inc , Englewood Cliffs, NJ 1979
Keely, J F and Kwasi Boateng, “Monitoring Well
Installation, Purging, and Sampling Techniques - Part
I Conceptualizations”, Groundwater V25, No 3,
1987 pp 300-313
Keely, J F and Kwas i Boateng, “Monitoring Well
Installation, Purging, and Sampling Techniques - Part
2 Case Histories”, Groundwater V25, No 4, 1987 pp
427-439
Well diameter 2”
Volume (gal/ft) 0 1632
4 !!
03672 06528 14688
where
h
cf
4
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CONTROLLED PUMPING TEST
SOP#: 204
DATE’ 10/04/94
REV #‘ 0.0
1.0 SCOPE AND APPLICATION
The most reliable arid commonly used method of
determining aquifer characteristics is by controlled
aquifer pumping tests Groundwater flow varies in
space and time and depends on the hydraulic
properties of the rocks and the boundaiy conditions
imposed on the groundwater system Pumping tests
provide results that are more representative of aquifer
characteristics than those predicted by slug or bailer
tests Pumping tests require a greater degree of
activity and expense, however, and are not always
justified for all levels of investigation As an
example, slug tests may be acceptable at the
reconnaissance level whereas pumping tests are
usually performed as part of a feasibility study in
support of designs for aquifer remediation
Aquifer charactenstics which may be obtained from
pumping tests include hydraulic conductivity (K),
Iransmlssivlty (T), specific yield (Sy) for unconfined
aquifers, and storage coefficient (S) for confined
aquifers These parameters can be determined by
graphical solutions and computerized programs The
purpose of this standard operating procedure (SOP) is
to outline the protocol for conducting controlled
pumping test
These are standard (i e, typically applicable)
operating procedures which may be vaned or changed
as required, dependent on site conditions, equipment
limitations or limitations imposed by the procedure or
other procedure limitations In all instances, the
ultimate procedures employed should be documented
and associated with the final report
Mention of trade names or commercial products does
not constitute U S EPA endorsement or
recommendation for use
2.0 METHOD SUMMARY
It is desirable to monitor pre.test water levels at the
test site for about one week prior to performance of
the pump test This information allows for the
determination of the barometric efficiency of the
aquifer, as well as noting changes in head, due to
recharging or pumping in the area adjacent to the well
Pnor to initiating the long term pump test, a step test
is conducted to estimate the greatest flow rate that
may be sustarned by the pump well
After the pumping well has recovered from the step
test, the long term pumping test begins At the
beginning of the test, the discharge rate is set as
quickly arid accurately as possible The water levels
in the pumping well and observation wells are
recorded accordingly with a set schedule Data is
entered on the Pump/Recovery Test Data Sheet
(Appendix A) The duration of the test is
determinated by project needs and aquifer properties,
but rarely goes beyond three days or until water levels
become constant
3.0 SAMPLE PRESERVATION,
CONTAINERS, HANDLING,
AND STORAGE
This section is not applicable to this SOP
4.0 iNTERFERENCES
POTENTIAL PROBLEMS
AND
Interferences and potential problems include
atmospheric conditions, impact of local potable wells,
and compression of the aquifer due to trains, heavy
ITaffic, etc
5.0 EQUIPMENT/APPARATUS
The following equipment is required to perform a
pump test
C Tape measure (subdivided into tenths of feet)
C Submersible pump
-------
C Water pressure transducer
C Electric water level indicator
C Weighted tapes
C Steel tape (subdivided into tenths of feet)
C Generator
C Electronic data-logger (if transducer method
is used)
C Watch or stopwatch with second hand
C Semi-log graph paper (if required)
C Water proof ink pen and logbook
C Thermometer
C Appropriate references and calculator
C A barometer or recording barograph (for tests
conducted in confined aquifers)
C Heat shrinks
C Electrical tape
C Flashlights and lanterns
C p1-1 meter
C Conductivity meter
C Discharge pipe
C Flow meter
6.0 REAGENTS
No chemical reagents are used for this procedure,
however, decontamination solutions may be
necessary If decontamination of equipment is
required, refer to the SOP for Sampling Equipment
Decontamination and the site specific work plan
7.0 PROCEDURES
7.1 Preparation
Determme the extent of the sampling effort,
the sampling methods to be employed, and
the types and amounts of equipment and
supplies needed
2 Obtain necessary sampling and monitoring
equipment
3 Decontaminate or preclean equipment, and
ensure that it is in working order
4 Prepare scheduling and coordinate with staff,
clients, and regulatory agency, if appropriate
5 Perform a general site survey prior to site
entry in accordance with the site specific
Health and Safety Plan
6 Identify and mark all sampling locations
7.2 Field Preparation
Review the site work plan and become
familiar with information on the wells to be
tested
2 Check and ensure the proper operation of all
field equipment Ensure that the electronic
data-logger is fully charged, if appropriate
Test the electronic data-logger using a
container of water Always bring additional
transducers in case of malfunctions
3 Assemble a sufficient number of field data
forms to complete the field assignment
4 The pumping well should be properly
developed pnor to testing, following the
guidelines outlined in the Well Development
SOP
5 An orifice, weir, flow meter, container or
other type of water measuring device to
accurately measure and monitor the
discharge from the pumping well shall be
provided
6 Sufficient pipe to transport the discharge
from the pumping well to an area beyond the
expected cone of depression is needed
Conducting a pumping test in contaminated
groundwater may require treatment, special
handling, or a discharge permit before the
water can be discharged
7 The discharge pipe must have a gate valve to
control the pumping rate
8 Determine if there is an outlet near the well
head for water quality determinauon and
sampling
7.3 Pre-Test Monitoring
It is desirable to monitor pretest water levels at the
test site for about one week prior to performance of
the test This can be accomplished by using a
continuous-recording device such as a Stevens
Recorder This information allows the determination
of the barometric efficiency of the aquifer when
2
-------
barometric records are available It also helps
determine if the aquifer is experiencing an increase or
decrease in head with time due to recharge or
pumping in the nearby area, or diurnal effects of
evapotranspiration Changes in barometric pressure
are recorded during the test (preferably with an on-site
barograph) in order to correct water levels for any
possible fluctuations which may occur due to
changing atmosphenc> conditions Pretest water level
trends are projected for the duration of the test These
trends and/or barometric changes are used to “correct”
water levels during the test so they are representative
of the hydraulic response of the aquifer due to
pumping of the test well
7.4 Step Test
TABLE 2 Time Intervals for Measuring Drawdown
in an Observation Well
Elapsed Time Since
Start or Stop of Test
(Minutes)
Interval Between
Measurements
(Minutes)
0-60
2
60-120
5
120-240
10
240-360
30
360-1440
60
1440-termination
480
7.5 2 Water Level Measurements
Pnor to initiating a long term pumping test, a step test
shall be conducted The purpose of a step test is to
estimate the greatest flow rate that may be sustained
during a long term test The test shall be performed
by progressively increasing the flow rate on one hour
intervals The generated drawdown versus time data
is plotted on semiloganthmic graph paper, and the
discharge rate is determined from this graph
7.5 Pump Test
7 5 1 Time Intervals
After the pumping well has fully recovered from the
step test, the long term pumping test may start At the
beginning of the test, the discharge rate should be set
as quickly and accurately as possible The water
levels in the pumping well and observation wells will
be recorded according to the following schedule
TABLE 1. Time Intervals for Measuring Drawdown
in the Pumped Well
Elapsed Time Since
Start or Stop of Test
(Minutes)
Interval Between
Measurements
(Minutes)
0-10
5-I
10-15
1
15-60
5
60-300
30
300-1440
60
1440-termination
480
Water levels will be measured as specified in the Well
Level Measurement SOP During the early part of the
test, sufficient personnel should be available to have
at least one person at each observation well and at the
pumping well After the first two hours, two people
are usually sufficient to continue the test It is not
necessary that readings at the wells be taken
simultaneously It is very important that depth to
water readings be measured accurately and readings
recorded at the exact time measured Alternately,
individual pressure transducers and electronic data-
loggers may be used to reduce the number of field
personnel hours required to complete the pumping
test A typical aquifer pump test form is shown in
Appendix A
During a pumping test, the following data must be
recorded accurately on the aquifer test data form
Site ID - A number assigned to identify a
specific site
2 Location - The location of the well in which
water level measurements are being taken
3 Distance from Pumped Well - Distance the
observation well is from the pumping well in
feet
4 Logger - The company conducting the
pumping test
5 Test Start Date - The date when the pumping
test began
3
-------
6 Test Start Time - Start time, using a 24-hour
clock
7 Static Water Level (Test Start) - Depth to
water, in feet and tenths of feet, in the
observation well at the beginning of the
pumping test
8 Test End Date - The date when the pumping
test was completed
9 Test End Time - End time, using a 24-hour
clock
10 Static Water Level (Test End) - Depth to
water, in feet and tenths of feet, in the
observation well at the end of the pumping
test
11 Average Pumping Rate - Summation of all
entries recorded in the Pumping Rate
(gal/mm) column divided by the total number
of Pumping Rate (gal/mm) readings
12 Measurement Methods - Type of instrument
used to measure depth-to-water (this may
include steel tape, electric sounding probes,
Stevens recorders, or pressure transducers)
13 Comments - Appropriate observations or
information which has not been recorded
elsewhere, including notes on sampling
14 Elapsed Time (mm) - Time of measurement
record continuously from time 0 00 (start of
test) recorded in minutes
15 Depth to Water (ft) - Depth to water, in feet
and tenths of feet, in the observation well at
the time of the water level measurement
16 Pumping Rate (gal/rn in) - Flow rate of pump
measured from an onfice, weir, flow meter,
container or other type of water measuring
device
7 53 Test Duration
The duration of the test is determined by the needs of
the project and properties of the aquifer One simple
test for detenninmg adequacy of data is when the log-
time versus drawdown for the most distant
observation well begins to plot as a straight line on the
semi-log graph paper There are several exceptions to
this simple rule of thumb, therefore, it should be
considered a minimum criteria Different
hydrogeologic conditions can produce straight line
trends on log-time versus drawdown plots In general,
longer tests produce more definitive results A
duration of one to three days is desirable, followed by
a similar penod of monitoring the recovery of the
water level Unconfined aquifers and partially
penetrating wells may have shorter test durations
Knowledge of the local hydrogeology, combined with
a clear understanding of the overall project objectives
is necessary in interpreting just how long the test
should be conducted There is no need to continue the
test if the water level becomes constant with time
This normally indicates that a hydrogeologic source
has been intercepted and that additional useful
information will not be collected by continued
pumping
7.6 Post Operation
The following activities shall be performed after
completion of water level recovery measurements
Decontaminate and/or dispose of equipment
as per the Sampling Equipment
Decontamination SOP
2 When using an electronic data-logger, use
the following procedures
C Stop logging sequence
C Print data, or save memory and
disconnect battery at the end of the
day’s activities
3 Replace testing equipment in storage
containers
4 Check sampling equipment and supplies
Repair or replace all broken or damaged
equipment
5 Review field forms for completeness
6 Interpret pumping/recovery test field results
8.0 CALCULATIONS
There are several accepted methods for determining
4
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aquifer properties such as transmissivity, storativity,
and conductivity However, the method to use is
dependent on the characteristics of the aquifer being
tested (confined, unconfined, leaky confining layer
etc) When reviewing pump test data the following
texts may be used to determine the method most
appropriate to your case
C Applied 1-lydrogeology (Fetter, 1980)
C Groundwater and Wells (Dnscoll, 1986)
C Groundwater (Freeze & Cheriy, 1979)
9.0 QUALITY ASSURANCEI
QUALITY CONTROL
All gauges, transducers, flow meters, and other
equipment used in conducting pumping tests shall be
calibrated before use at the site Copies of the
documentation of instrumentation calibration should
be obtained and filed with the test data records The
calibration records will consist of laboratory
measurements and, if necessary, any on-site zero
adjustment and/or calibration will be performed
Where possible, all flow and measurement meters will
be checked on-site using a container of measured
volume and stopwatch, the accuracy of the meters
must be verified before testing proceeds
10.0 DATA VALIDATION
This section is not applicable to this SOP
11.0 HEALTH AND SAFETY
When working with potentially hazardous materials,
following U S EPA, OSHA, and corporate health and
safety practices
12.0 REFERENCES
Boulton, N S, 1954 The Drawdown of the Water-
Table under Non-Steady Conditions Near a Pumped
Well in an Unconfined Formation”, Paper 5979 in
Proceedings of the Institution of Civil Engineers, Vol
3, p 564
Boulton, N S, 1963 Analysis of Data from Non-
Equilibrium Pumping Tests Allowing for Delayed
Yield from Storage”, Paper 6693 in Proceedings of the
Institution of Civil Engineers, Vol 26, pp 469-82
Bower, H, 1978 Groundwater Hydrology, McGraw-
Hill Book Company, New York, New York
Bower, H and R C Rice, 1976 A Slug Test for
Determining Hydraulic Conductivity of Unconfmed
Aquifers with Completely or Partially Penetrating
Wells, Water Resources Research, Vol 12, No 3
Bredehoeft, JD and S S Papadopulos, 1980 A
Method of Determining the Hydraulic Properties of
tight Formations’, Water Resources Research, Vol
16,No “pp 233-238
Cooper, Jr H H, J D, Bredehoeft, and S S
Papadopulos, 1967 “Response of a Finite-Diameter
Well to an Instantaneous Charge of Water’, Water
Resources Research, Vol 13, No I
Cooper, Jr, 1-I H, and C E, Jacob, 1946 “A
Generalized Graphical Method for Evaluating
Formation Constants and Summarizing Well-Field
History”, American Geophysical Union Transactions,
Vol 27, No 4, pp 526-534
Earlougher, R C , 1977 Advances in Well Test
Analysis, Society of Petroleum Engineers of AIME
Ferns, J G, and D B, Knowles, 1954 “The Slug
Test for Estimating Transmissivity”, US Geological
Survey Ground Water Note 26
5
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APPENDIX A
Pump/Recovery Test Data Sheet
PAGE OF
PUMP/RECOVERY TEST DATA SHEET
SITE ID DISTANCE FROM PUMPED WELL (FT)
LOCATION LOGGER
TEST START TEST END
DATE DATE
TIME TIME
STATIC WATER LEVEL (FT) — STATIC WATER LEVEL (FT) —
AVERAGE PUMPING RATE (GAL/MIN)
MEASUREMENT METHODS
COMMENTS
PUMP TEST
RECOVERY TEST
ELAPSED TIME
DEPTH TO
PUMPING RATE
ELAPSED TIME
DEPTH TO
(MIN)
WATER (FT)
(GALIMIN)
(MIN)
WATER (FT)
000
000
6
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APPENDIX A (Cont’d)
Pump/Recovery Test Data Sheet
PAGE OF
PUMP/RECOVERY TEST DATA
SITE
LOCATION ID DATE
PUMP TEST
RECOVERY TEST
ELAPSED TIME
DEPTH TO
PUMPING RATE
ELAPSED TIME
DEPTH TO
(MIN)
WATER (FT)
(GAL/MIN)
(MIN)
WATER (FT)
000
000
7
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SLUG TESTS
SOP#: 204i
DATE 10/03/94
REV.#: 00
1.0 SCOPE AND APPLICABILITY
This procedure is applicable to determine the
horizontal hydraulic conductivity of distinct geologic
horizons under rn-situ conditions The hydraulic
conductivity (K) is an important parameter for
modeling the flow of groundwater m an aquifer
These are standard (i e typically applicable) operating
procedures which may be varied or changed as
required, dependent upon site conditions, equipment
limitations or limimtations imposed by the procedure
In all instances, the ultimate procedures employed
should be documented and associated with the final
report
Mention of trade names or commercial products does
not constitute U S Environmental Protection Agency
(U S EPA) endorsement or recommendation for use
2.0 METHOD SUMMARY
A slug test involves the instantaneous injection or
withdrawal of a volume or slug of water or solid
cylinder of known volume This is accomplished by
displacing a known volume of water from a well and
measuring the artificial fluctuation of the groundwater
level
The primary advantages of usrng slug tests to estimate
hydraulic conductivities are numerous First,
estimates can be made in-situ, thereby avoiding errors
incurred in laboratory testing of disturbed soil
samples Second, tests can be performed quickly at
relatively low costs because pumping and observation
wells are not required And lastly, the hydraulic
conductivity of small discrete portions of an aquifer
can be estimated (e g , sand layers in a clay)
3.0 SAMPLE PRESERVATION,
CONTAINERS, HANDLING AND
STORAGE
This section is not applicable to this standard
operating procedure (SOP)
4.0 INTERFERENCES
POTENTIAL PROBLEMS
AND
Limitations of slug testing include I) only the
hydraulic conductivity of the area immediately
surrounding the well is estimated which may not be
representative of the average hydraulic conductivity of
the area, and 2) the storage coefficient, S, usually
cannot be determined by this method
5.0 EQUIPMENT/APPARATUS
The following equipment is needed to perform slug
tests All equipment which comes in contact with the
well should be decontaminated and tested prior to
commencing field activities
C Tape measure (subdivided into tenths of feet)
C Water pressure transducer
C Electric water level indicator
C Weighted tapes
C Steel tape (subdivided into tenths of feet)
C Electronic data-logger (if transducer method
is used)
C Stainless steel slug of a known volume
C Watch or stopwatch with second hand
C Semi-log graph paper (if required)
C Water proof ink pen and logbook
C Thermometer
C Appropriate references and calculator
C Electrical tape
C 2lX micrologger
C Compact portable computer or equivalent
with Grapher installed on the hard disk
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6.0 REAGENTS
No chemical reagents are used in this procedure,
however, decontamination solvents may be necessary
If decontamination of the slug or equipment is
required, refer to the Sampling Equipment
Decontamination SOP and the site specific work plan
7.0 PROCEDURES
7.1 Field Procedures
The following general procedures may be used to
collect and report slug test data These procedures
may be modified to reflect site specific conditions
When the slug test is performed using an
electronic data-logger and pressure
transducer, all data will be stored internally
or on computer diskettes or tape The
inforrnauon will be transferred directly to the
main computer and analyzed A computer
printout of the data shall be maintained in the
files as documentation
lithe slug test data is collected and recorded
manually, the slug test data form (Figure 1,
Appendix A) will be used to record
observations The slug test data form shall
be completed as follows
C Site ID - Identification number
assigned to the site
C Location ID - Identification of
location being tested
C Date - The date when the test data
was collected in this order year,
month, day (eg, 900131 for
January 31, 1990)
C Slug volume (ft 3 ) - Manufacturers
specification for the known volume
or displacement of the slug device
C Logger - identifies the company or
person responsible for performing
the field measurements
C Test method - The slug device is
either injected or lowered into the
well or withdrawn or pulled-out
from the monitor well Check the
method that is applicable to the test
situation being run
C Comments Appropriate
observations or information for
which no other blanks are provided
C Elapsed time (mm) - Cumulative
time readings from beginning of test
to end of test, in minutes
C Depth to water (It) - Depth to water
recorded in tenths of feet
2 Decontaminate the transducer and cable
3 Make initial water level measurements on
monitor wells in an upgradient to
down gradient sequence, if possible
4 Before beginning the slug test, information
will be recorded and entered into the
electronic data-logger The type of
information may vary depending on the
model used When using different models,
consult the operator’s manual for the proper
data entry sequence to be used
5 Test wells from least contaminated to most
contaminated, if possible
6 Determine the static water level in the well
by measuring the depth to water periodically
for several minutes and taking the average of
the readings
7 Cover sharp edges of the well casing with
duct tape to protect the transducer cables
8 Install the transducer and cable in the well to
a depth below the target drawdown estimated
for the test but at least two feet from the
bottom of the well Be sure the depth of
submergence is within the design range
stamped on the transducer Temporarily tape
the transducer cable to the well to keep the
transducer at a constant depth
9 Connect the transducer cable to the electronic
data-logger
10 Enter the initial water level and transducer
design range into the recording device
according to manufacturers instructions (the
transducer design range will be stamped on
the side of the transducer) Record the initial
water level on the recording device
II “Instantaneously” introduce or remove a
2
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known volume or slug of water to the well
Another method is to introduce a solid
cylinder of known volume to displace and
raise the water level, allow the water level to
restabilize and remove the cylinder It is
important to remove or add the volumes as
quickly as possible because the analysis
assumes an “instantaneous” change in
volume is created in the well
12 At the moment of volume addition or
removal assigned time zero, measure and
record the depth to water and the time at each
reading Depths should be measured to the
nearest 001 foot The number of depth-time
measurements necessary to complete the test
are variable It ES critical to make as many
measurements as possible in the early part of
the test The number and intervals between
measurements will be determined from
earlier previous aquifer tests or evaluations
13 Continue measuring and recording
depth-time measurements until the water
level returns to equilibrium conditions or a
sufficient number of readings have been
made to clearly show a trend on a semi-log
plot of time versus depth
14 Retrieve slug (if applicable)
The time required for a slug test to be
completed is a function of the volume of the
slug, the hydraulic conductivity of the
formation and the type of well completion
The slug volume should be large enough that
a sufficient number of water level
measurements can be made before the water
level returns to equilibrium conditions The
length of the test may range from less than a
minute to several hours
lithe well is to be used as a monitoring well,
precautions should be taken that the wells are
not contaminated by material introduced into
the well If water is added to the monitoring
well, it should be from an uncontaminated
source and transported in a clean container
Batters or measuring devices should be
cleaned prior to the test If tests are
performed on more than one monitor well,
care must be taken to avoid cross
contamination of the wells
Slug tests shall be conducted on relatively
undisturbed wells If a test is conducted on
a welt that has recently been pumped for
water sampling purposes, the measured water
level must be withm 0 I foot of the water
level prior to sampling At least one week
should elapse between the drilling of a well
and the performance of a slug test
7.2 Post Operation Procedures
When using an electronic data-logger use the
following procedure
Stop logging sequence
2 Print data
3 Send data to computer by telephone
4 Save memory and disconnect battery at the
end of the day’s activities
5 Review field forms for completeness
8.0 CALCULATIONS
The simplest interpretation of piezometer recovery is
that of Hvorslev (1951) The analysis assumes a
homogenous, isotropic medium in which soil and
water are incompressible Hvorslev’s expression for
hydraulic conductivity (K) is
K • r In (LIR ) for LIR> 8
2 L T 0
= hydraulic conductivity [ ftlsec]
= casing radius [ ft]
= length of open screen (or borehole)
[ ft]
= filter pack (borehole) radius (ft]
= Basic Time Lag [ sec], value oft on
semi-logarithmic plot of H-h/H-H 0
vs t. where H-h/Fl-H 0 = 0 37
initial water level pnor to removal
of slug
= waterlevelatt=0
= recorded water level at I > 0
(Hvorslev, 1951, Freeze and Cherry, 1979)
where
K
r
L
R
To
H
‘I
3
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The Bower and Rice method is also commonly used
for K calculations However, it is much more time
consuniuig than the Hvorslev method Refer to Freeze
and Cheny or Applied Hydrogeology (Fetter) for a
discussion of these methods
9.0 QUALITY ASSURANCEI
QUALITY CONTROL
The following general quality assurance procedures
apply
All data must be documented on standard
Chain of Custody records, field data sheets,
or within personal/site logbooks
2 All instrumentation must be operated in
accordance with operating instructions as
supplied by the manufacturer, unless
otherwise specified in the work plan
Equipment checkout and calibration
activities must occur prior to
sampling/operation, and they must be
documented
The following specific quality assurance activity will
apply
Each well should be tested at least twice in
order to compare results
10.0 DATA VALIDATION
This section is not applicable to this SOP
11.0 HEALTH AND SAFETY
When working with potential hazardouse materials,
follow U S EPA, OSl-TA and corporate health and
safety procedures
12.0 REFERENCES
Bower, H, 1978 Groundwater Hydrology,
McGraw-I-hi] Book Company, New York, New York
Bower, H, and R C Rice, 1980 “A Slug Test for
Determining the Hydraulic Properties of Tight
Fonnations’, Water Resources Research, Vol 16, No
1 pp 233-238
Cooper, Jr H H, 3 D, Bredehoeft, and S S
Papadopulos, 1967 ‘Response of a Finite-Diameter
Well to an Instantaneous Charge of Water , Water
Resources Research, Vol 13,No I
DOT (U S Department of the Interior), Ground Water
Manual, U S Government Printing Office, New York,
New York, Washington, D C
Earlougher, R C , 1977 Advances in Well Test
Analysis, Society of Petroleum Engineers of AIME
Ferns, J G, and D B, Knowles, 1954 “The Slug
Test for Estimating Transmissivity”, U S Geological
Survey Ground Water Note 26
Freeze, R Allen and John A Cherry, 1979
Groundwater, Prentice-Hall, Inc , Englewood Cliffs,
New Jersey
Hvorslev, 1951 ‘Time Lag and Soil Permeability in
Ground Water Observations”, Bulletin No 36, U S
Army Corps of Engineers p 50
Johnson Division, UOP, Inc , 1966 Ground Water
and Wells, Johnson Division, UOP, Inc., St Paul,
Minnesota
Lohman, S W , 1982 “Ground Water Hydraulics”,
U S Geological Survey, Paper 708, p 70
Neuman, S F, 1972 “Theory of Flow in Unconfined
Aquifers Considenng Delayed Response of the Water
Table”, Water Resources Research, Vol 8, No 4, p
1031
Papadopulos, S S. J D, Bredehoeft, H H, Cooper,
Jr. 1973 “On the Analysis of Slug Test Data”, Water
Resources Research, Vol 9, No 4
Todd, David K, 1980 Ground Water Hydrology, 2nd
ed John Wiley & Sons
4
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APPENDIX A
Slug Test Data Form
Page_ of_
FIGURE 1 Slug Test Data Form
DATE _____________________
SITE ID _______________________ SLUG VOLUME (ft 3 ) ___________
LOCATION ID _____________ LOGGER ______________
TEST METHOD — SLUG INJECTION — SLUG WITHDRAWAL
COMMENTS __________________
Time Beginning of Test #1
Time End of Test #1
Time Beginning of Te
Time End of Test #2
st #2
ELAPSED TIME
DEPTH TO
ELAPSED TIME
DEPTH TO
(MIN)
WATER (FT)
(MIN)
WATER (FT)
5
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MONITOR WELL
INSTALLATION
SOP 2041
DATE 03/18/96
REV. # 0.0
1.0 SCOPE AND APPLICATION
The purpose of this standard operating procedure
(SOP) is to provide an overview of the methods used
for groundwater monitor wells Monitor well
installation create permanent access for collection of
samples to assess groundwater quality and the
hydrogeologic properties of the aquifer in which
contaminants may exist Such wells should not alter
the medium which is being monitored
The most commonly used drilling methods are the
hollow-stem auger, cable tool, and hydraulic rotary
Rotary drilling can utilize mud rotary or air rotary
methods
These are standard (i e , typically applicable)
operating procedures which may be varied or changed
as required, depending on site conditions, equipment
limitations, or limitations imposed by the procedures
themselves In all instances, the ultimate procedures
employed should be documented and desenbed in the
final report as well as in logbooks
Mention of trade names or commercial products does
not constitute United States Environmental Protection
Agency (U S EPA) endorsement or recommendation
for use
2.0 METHOD SUMMARY
There is no ideal monitor well installation method for
all conditions therefore, hydrogeologic conditions at
the site as well as project objectives must be
considered before deciding which drilling method is
appropriate
2.1 Hollow-Stem Augering
Outside diameters of hollow-stem augers generally
range from 6 1/4 inches to 22 inches with
corresponding inner diameters ranging from 2 1/4
inches to 13 inches Auger lengths are usually 5 feet
which allows easy handling However, lengths of 10
or 20 feet may be used for deeper holes drilled with
machines capable of handling the extended lengths
Formation samples can be taken in a number of ways,
depending on the accuracy required Cuttings may
suffice for shallow depths but become less
representative with depth, particularly below the water
table The most accurate samples are obtained with
various coring devices, such as split spoons or shelby
tubes which can be used inside the augers
Continuous cores can also be taken with a thin-walled
tube which is inserted into the lowest auger and
locked in place The tube is retracted with a wire line
and hoist after the hole has been advanced the length
of the auger A bottom plug in the cutting head or bit
prevents cuttings from entering the augers until the
first core sample is taken and the plug is knocked out
In unconsolidated material, the augers serve as a
temporary casing and gravel-packed wells can be
constructed inside the augers and then the augers
withdrawn Well development is usually less difficult
than with wells drilled by the mud rotary method
because a bentonite dnlling fluid is not normally used
2.2 Cable Tool Drilling
Cable tool drilling is a percussion method in which a
bit, attached to a drilling string, is lifted and dropped
The drilling siring, consists (bottom to top) of the bit,
drill stem, drilling jars, socket, and wire cable A
walking beam on the drilling rig provides the lifting
and dropping motion to the wire cable and hence to
the drilling string The repeated action breaks or
loosens the formation material which mixes with
formation water or water added to the hole by the
operator to form a slurry The slurry facilitates
removal of the cuttings which are periodically
removed from the hole with a bailer In
unconsolidated formations, steel casing roust be
driven or pushed into the ground as the drilling
progresses in order to prevent hole collapse A
hardened steel drive shoe on the bottom end of the
-------
casing prevents damage during driving A well may
then be constructed inside the steel casing and the
casing pulled back In consolidated formations, the
casing may be dnven through the weathered zone, and
seated in solid rock The hole below the casing may
remam open or may be fitted ‘with a smaller diameter
inner casing and screen, depending on the sampling
requirements Depending on formation material,
extensive well development may often not be
necessary
2.3 Rotary Drilling
2 3 1 Mud Rotary Method
In the mud rotary method the drill bit is rotated rapidly
to cut the formation material and advance the
borehole The drill bit is anached to hollow dulling
rods which transfer power from the rig to the bit In
conventional rotary drilling, cuttings are removed by
pumping drilling fluid (water, or water mixed with
bentonite or other additives) down through the drill
rods and bit, and up the annulus between the borehole
and the drill rods The drilling fluid flows into a mud
pit where the cuttings settle out and then is pumped
back down the drill rods The drilling fluid also cools
the bit and prevents the borehole from collapsing in
unconsolidated formations
Sampling may be done from the cuttings but samples
are generally mixed and the amount of fine material
may not be accurately represented Coring may be
done through the drill rods and bit if a coring bit (with
a center opening big enough to allow passage of the
coring tube) is used When drilling unconsolidated
formations, a temporary surface or shallow casing
may have to be installed in order to prevent cross-
contamination, hole collapse, or wall erosion by the
dnlling fluid Casing (riser pipe), screen, and gravel
pack are usually installed in the open hole or through
the surface casing Once the well is constructed,
extensive well development may be necessary in order
to remove drilling fluid from the formation
2.3 2 Air Rotary Method
The air rotary method uses air as the drilling fluid
Air is forced down the drill rods by an air compressor,
escapes out of the bit and returns to the surface in the
annular space between the hole wall and the drill
string Cuttings are moved out of the hole by the
ascending air and collect around the rig Cuttings are
mixed and may not always be representative of the
depth currently being drilled In the conventional air
rotary method, the drill string operates in a manner
similar to that dcscnbed for the mud rotary system In
a “hammer” or ‘down-the-hole air rotary method, the
bit is pneumatically driven rapidly against the rock in
short strokes while the drilling string slowly rotates
The use of air rotary methods are generally limited to
consolidated and semi-consolidated formations
Casing is often used in semi-consolidated formations
and through the weathered portion of consolidated
formations to prevent hole collapse In environmental
work, the air supply must be filtered to prevent
introduction of contamination into the borehole
3.0 SAMPLE PRESERVATION,
CONTAINERS, HANDLING,
AND STORAGE
Often, a primary objective of the drilling program is to
obtain representative hthologic or environmental
samples The most common techniques for retrieving
samples are
In unconsolidated formations
C Split spoon sampling, camed out
continuously or at discrete intervals during
drilling, as summarized in ASTM Method D-
1586-84, Split Barrel Sampling
C Shelby tube sampling when an undisturbed
sample is required from clayey or silty soils,
especially for geotechnical evaluation or
chemical analysis
C Cutting collection when a general lithologic
description and approximate depths are
sufficient
In consolidated formations
C Rock conng at continuous or discrete
intervals
C Cutting collection when a general lithologic
description and approximate depths are
sufficient
When collecting environmental samples, the amount
of sample to be collected and the proper sample
container type (i e , glass, plastic), chemical
preservation, and storage requirements are dependent
on the matrix being sampled and the parameter(s) of
interest Sample preservation, containers, handling
2
-------
and storage for air and waste samples are discussed in
the specific SOPs for the technique selected
4.0 INTERFERENCES AND
POTENTIAL PROBLEMS
Advantages and disadvantages of the various drilling
methods are summarized below
4.1 Auger Drilling
The advantages of auger drilling are
C Relatively fast and inexpensive
C Because augers act as temporary casing,
drilling fluids are not used resulting in
reduced well development
The disadvantages of auger drilling are
C Very slow or impossible to use in coarse
materials such as cobble or boulders
C Cannot be used m consolidated formations
and is generally limited to depths of
approximately 100 feet in order to be
efficient
4.2 Cable Tool Drilling
The advantages of cable tool drilling are
C Relatively inexpensive with minimum labor
requirements
C The water table and water beanng zones are
easily identified
C Driven casing stabilizes borehole and
minimizes potential for cross-contamination
C Especially successful in drilling caving
formations or formations containing boulders
C Accurate formation samples can usually be
obtained from cuttings
The disadvantages of cable tool drilling are
C Extremely slow rate of drilling
C Necessity to drive casing may limit depth in
large diameter holes
4.3 Rotary Drilling
4,3 1 Mud Rotary Drilling
The advantages of mud rotary dnlling are
C Fast, more than 100 feet of borehole
advancement per day is common
C Provides an open borehole, necessary for
some types of geophysical logging and other
tests
The disadvantages of mud rotary drilling are
C Potential for cross-contamination of water-
bearing zones
C Drill cuttings may be mixed and not
accurately represent lithologies at a given
drilling depth
C Drilling mud may alter the groundwater
chemistry
C Water levels can only be determined by
constructing wells
C Drilling mud may change local permeability
of the formation and may not be entirely
removed dunng well development
C Disposal of large volumes of drilling fluid
and cuttings may be necessary if they are
contaminated
4.3.2 Air Rotary Drilling
The advantages of air rotary drilling are
C Fast, more than 100 feet of borehole
advancement a day is possible
C Preliminary estimates of well yields and
water levels are often possible
C No drilling fluid to plug the borehole
The disadvantages of air rotary drilling are
3
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C Generally cannot be used in unconsolidated
formations
C In contaminated zones, the use of high-
pressure air may pose a significant hazard to
the dnll crew because of transport of
contaminated matenal up the hole
C Introduction of air to the groundwater could
reduce concentration of volatile organic
compounds
5.0 EQUIPMENT
The following equipment is necessary for the site
geologist
C Metal clipboard box case (container for
well logs)
C Ruler
C Depth sounder
C Water level indicator
C All required health and safety gear
C Sample collection jars
C Trowels
C Description aids (Munsell color chart, grain
size charts, etc )
C Geolis® Logbooks (Appendix A)
C Field Logbook
Equipment and tools to install the well are normally
provided by the drilling contractor
6.0 REAGENTS
Reagents are not required for preservation of soil
samples Samples should, however, be cooled to 4 C
and protected from sunlight in order to minimize any
potential reaction due to the light sensitivity of the
sample Decontamination of drilling equipment
should follow the Sampling Equipment
Decontamination SOP and the site-specific work
plan
7.0 PROCEDURES
7.1 Preparation
All drilling and well installation programs must be
planned and supervised by a professional
geologist/hydrogeologist
The planning, selection and implementation of any
monitor well installation program should include the
foil os;’ i ng
C Review of existing data on site geology and
hydrogeology including publications, air
photos, water quality data, and existing
maps These may be obtained from local,
state or federal agencies
C Assesment of the site to determine potential
access problems for drill rig, locate water
supply sources, establish equipment storage
area, and observe outcrops
C Perform utilities check, note location of
underground utilities and of overhead
electrical wires
C Preparation of a Site Safety Plan
C Select dnlling, sampling and
development methods
well
C Determination of well construction
specifications (i e , casing and screen
matenals, casing and screen diameter, screen
length and screen interval, filter pack and
screen slot size)
C Determination of the need for containing dnll
cuttings and fluids and their method of
disposal
C Preparation of work plan includmg all of the
above
C Preparation of and execute the drilling
contract
7.2 Field Preparation
Prior to mobilization, the drill rig and all associated
equipment should be thoroughly decontaminated by a
steam/pressure washer to remove all oil, grease, mud,
etc Before drilling each boring, all the “down-the-
hole” drill equipment should be steam cleaned and
rinsed with potable water to niiriimizc cross-
contamination Special attention should be given to
the threaded section of the casings, and to the dnli
rods All drilling equipment should be steam-cleaned
at completion of the project to ensure that no
contamination is transported to or from the sampling
site
4
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7.3 Well Construction
The well casing material should not interact with the
groundwater Well casings for environmental projects
are usually constructed of polyvinyl chloride (PVC),
Teflon , fiberglass, or stainless steel Details of the
construction methods are given in Sections 7 3 1 and
7 3.2
7.3 1 Bedrock Wells
Wells completed in bedrock will be drilled using the
air or mud rotary method Ciystalline rock wells are
usually drilled most efficiently with the air rotary
method while consolidated sedimentary formations
are drilled using either the air rotary or mud rotary
method The compressed air supply will be filtered
prior to introduction into the borehole to remove oil or
other contaminants Bedrock wells may be completed
as an open-hole, providing that borehole cave-in is not
a possibility
Bedrock wells will be advanced with air or mud rotary
methods until a minunum of 5 feet of competent rock
has been dnlled Minimum borehole diameter will be
8 inches The dnll string will then be pulled from the
borehole and 6-inch I D Schedule 80 or 40 PVC
casing inserted Portland cement/bentornie grout will
be pumped into the hole and up the annular space
outside the casing After the grout has set (minimum
of 24 hours), the cement will be drilled out and the
borehole advanced to the desired depth Figure 1
(Appendix B) shows typical construction details for an
open-hole bedrock well
The preferred method of well completion for the
bedrock wells will be open-hole However, if the
open borehole is subject to cave-in, the well(s) will be
completed as screened and cased sand-packed wells
For details of completion see Section 7 3 2
7.3 2 Overburden Well Construction
Any of the drilling methods discussed in this SOP can
be used to drill or set a well in the overburden The
hollow-stem method is the preferred choice for
shallow (<100 ft) overburden wells because the well
can be constructed inside of the augers Details of the
construction are provided below and are shown in
Figure 2 (Appendix B)
The screen slot size will be determined by
the site hydrologist, based upon sand-pack
size The length of screen used will be site-
dependent Casing sections will be flush-
threaded Screw-threaded bottom plugs will
be used To prevent introduction of
contaminants inio the well, no glue.
connected fittings will be used Each piece
of PVC pipe, screen, and the bottom plug
will be steam-cleaned before lowering into
the borehole The site hydrogeologist is
responsible for the supervision of all steam
cleaning procedures
2 The annular space between the well screen
and the borehole wall will be filled with a
uniform gravellsand pack to serve as a filter
media For wells deeper than approximately
50 feet, or when recommended by the site
geologist, the sand pack will be emplaced
using a tremie pipe A sand slurry composed
of sand and potable water will be pumped
through the tremie pipe into the annulus
throughout the entire screened interval, and
over the top of the screen Allowance must
be made for settlement of the sand pack
3 The depth of the top of the sand will be
determined using the tremie pipe, thus
verifying the thickness of the sand pack
Additional sand shall be added to bring the
top of the sand pack to approximately 2 to 3
feet above the top of the well screen Under
no circumstances should the sand pack
extend into any aquifer other than the one to
be monitored In most cases, the well design
can be modified to allow for a sufficient sand
pack without threat of crossflow between
producing zones through the sand pack
4 In matenals that will not maintain an open
hole using hollow-stem augers, the
temporary or outer casing will be withdrawn
gradually during placement of sand
pack/grout For example, after filling two
feet with sand pack, the outer casing should
be withdrawn 2 feet This step of placing
more gravel and withdrawing the outer
casing should be repeated until the level of
the sand pack is approximately 3 feet above
the top of the well screen This ensures that
ihere is no locking of the permanent (inner)
casing in the outer casing
S
-------
8-10 gallons of water, if water mixed
5 A bentonite seal of a minimum 2-foot
vertical thickness will be placed in the
annular space above the sand pack to
separate the sand pack from the cement
surface seal The bentonite will be placed
through a tremie pipe or poured directly into
the annular space, depending upon the depth
and site conditions The bentonite will be
pourable pellets The hydrogeologust will
record the start and stop times of the
bentonite seal emplacement, the interval of
the seal, the amount of bentonite that was
used, and problems that arise The type of
bentoriite and the supplier will also be
recorded
A cap placed over the top of the well casing
before pouring the bentonite pellets will
prevent pellets from entering the well casing
6 If a slurry of bentonite is used as annular
seal, it is prepared by mixing powdered or
granular bentonite with potable water The
slurry must be of sufficiently high specific
gravity and viscosity to prevent its
displacement by the grout to be emplaced
above it As a precaution (regardless of
depth) and depending on fluid viscosity, a
few handfuls of bentonite pellets may be
added to solidify the bentonite slurry surface
7 Cement andior bentonite grout is placed from
the top of the bentonite seal to the giound
surface
Only Type I or II cement without accelerator
additives may be used An approved source
of potable water must be used for mixing
grouting materials The following mixes are
acceptable
C Neat cement, a maximum of 6 gallons of
water per 94 pound bag of cement
C Granular bentonite, 1 5 pounds of bentonite
per 1 gallon of water
£ Cement-bentornte, 5 pounds of pure
bentonite per 94 pound bag of cement with 7-
8 gallons of water
C Cement-bentomte, 6 to 8 pounds of pure
beritonite per 94 pound bag of cement with
C Non-expandable cement, mixed at 7 5
gallons of water to one half (112) teaspoon of
Aluminum 1-lydroxide, 94 pounds of neat
cement (Type I) and 4 pounds of bentonite
C Non-expandable cement, mixed at 7 gallons
of water to one half (1/2) teaspoon of
Aluminum Hydroxide, 94 pounds of neat
cement (Type I and Type II)
8 Grout is pumped through a tremie pipe
(normally a 1 25-inch PVC or steel pipe) to
the bottom of the annulus until undiluted
grout flows from the annulus at the ground
surface
9 In materials that will not maintain an open
hole, the temporary steel casing should be
withdrawn in a manner that prevents the
level of grout from dropping below the
bottom of the casing
10 Additional grout may be added to
compensate for the removal of the temporary
casing and the tremie pipe to ensure that the
top of the grout is at or above ground surface
After the grout has set (about 24 hours), any
depression due to settlement is filled with a
grout mix similar to that desenbed above
11 The protective casing should now be set
Casing may be a 5 foot minimum length of
black iron or galvanized pipe extending about
1 5 to 3 feet above the ground surface, and
set in concrete or cement grout The
protective casing diameter should be 4 inches
greater than the well casing A 0 5-inch drain
hole may be installed near ground level A
flush-mount protective casing may also be
used in areas of high liaffic or where access
to other areas would be limited by a well
stick -up
12 A protective steel cap, secured to the
protective easing by a padlock, should be
installed
13 Steel guard posts should be installed around
the protective casing in areas where vehicle
traffic may be a problem Posts should have
a minimum diameter of 3 inches and be a
6
-------
minimum of 4 feet high
14 All monitor wells should be labelled and
dated with paint or steel tags
7.4 Well Development
Well development is the process by which the
aquifer’s hydraulic conductivity is restored by
removing drilling fluids, and fine-grained formation
material from newly installed wells Two methods of
well development that are commonly used are surging
and bailing, and overpumping A well is considered
developed when the p 1 -I and conductivity of the
groundwater stabilizes and the measured turbidity is
<50 nephelometric turbidity units (NTUs)
Surging and bailin will be performed as follows
1 Measure the total depth (TD) of the well and
depth to water (DTW)
2 Using an appropriately sized surge block,
surge 5-foot sections of well screen, using
10-20 up/down cycles per section
Periodically remove the surge block and bail
accumulated sediment from the well, as
required
3 For open-hole wells, a 6-inch surge block
will be used inside the cased portion of the
well Sediments will be bailed periodically,
as required Overpurnping may be used in
combination with surging and bailing for
development of bedrock wells The
method(s) used will be based on field
conditions encountered, and will be
determined by the site hydrogeologist
However, sediment will initially be removed
from the wells by bailing in order to
minimize the volume of development water
generated
The pump used must be rated to achieve the desired
yield at a given depth The pump system should
include the following
C A check valve to prevent water from running
back into the well when the pump is shut off
C Flexible discharge hose
C Safety cable or rope to remove the pump
from the well
C Flow meter monitoring system (measuring
bucket or inline flow meter)
C Generator
C Amp meter, to measure electrical current
(load)
The amp meter is used to monitor pump performance
If the pump becomes clogged, the current will
increase due to stress on the pump If the water level
drops below the intake ports, the current will drop due
to decreased resistance on the pump
8.0 CALCULATIONS
To maintain an open borehole during rotary drilling,
the drilling fluid must exert a pressure greater than the
formation pore pressure Typical pore pressures for
unconfined and confined aquifers are 0 433 define
(psi/ft) and 0 465 psi/fl, respectively
The relationship for determining the hydrostatic
pressure of the drilling fluid is
Hydrostatic Pressure (psi) = Fluid Density (lb/gal) x
Height of Fluid Column (ft) x 0 052
The minimum grout volume necessary to grout a well
can be calculated using
Grout Vol (fl 3 ) = Vol of Borehole (ft 3 ) - Vol of Casing
(ft 3 ) = L (rB 2 - r 2 )
where
= length of borehole to be grouted (ft)
= radius of boring (ft)
= radius of casing (ft)
9.0 QUALITY ASSURANCE/
QUALITY CONTROL
There are no specific quality assurance activities that
apply to the implementation of these procedures
However, the following general QA procedures apply
All data must be documented on standard
well completion forms, field data sheets or
within field/site logbooks Descriptive logs,
pump tests, and well completion date are
entered on Geolis® forms The Geolis®
forms are used to ensure data is collected
uniformly by all Site Geologists and provide
L
rc
7
-------
input to a standardized computer well file
Appendix A contains examples of Geolis®
forms used to record descriptions of geologic
samples
2 All instrumentation must be operated in
accordance with operating instructions as
supplied by the manufacturer, unless
otherwise specified in the work plan
Equipment checkout and calibration
activities must occur prior to
samphng/operation and must be documented
10.0 DATA VALIDATION
This section is not applicable to this SOP
11.0 HEALTH AND SAFETY
Drilling ngs and equipment present a variety of safety
hazards REAC personnel working around dulling
ngs should know the position of the emergency “kill”
switch Wirehnes and ropes should be inspected and
frayed or damaged sections discarded Swivels and
blocks should turn freely Gages should be
operational and controls clearly marked All
underground utilities should be clearly marked, and
drillers should be aware of any overhead hazards such
as power lines Avoid drilling in these areas Ear
protection should be worn when working around
dnhling equipment for extended periods of time,
particularly air rotary equipment Failure to follow
safety procedure or wear the proper personal
protection gear on the part of either the drilling crew
or REAC personnel may result in dismissal from the
job
When working with potentially hazardous materials,
follow U S EPA, OSI-LA, and corporate health and
safety practices
12,0 REFERENCES
Amencan Society for Testing and Materials 1991
Annual Book of ASTM Standards Designation
D5092-90 Standard Practice for Design and
Installation of Groundwater Monitoring Wells in
Aquifers p 1081-1092 Philadelphia,PA
Boateng, K, P C Evens, and SM Testa 1984
“Groundwater Contamination of Two Production
Wells A Case History “ Groundwater Monitoring
Review, V 4, No 2, p 24-31
Keely, .T F and Kwasi Boateng 1987 “Monitonng
Well Installation, Purging, and Sampling Techniques-
Part I Conceptualizations” Groundwater V 25,
No 3,p 300-313
Keely, J F and Kwasi Boateng 1987 “Monitoring
Well Installation, Purging, and Sampling Techniques -
Part 2 Case Histories” Groundwater V 25, No 4,
p 427-439
Dnscoll, F G 1986 Groundwater and Wells (2nd
ed) Johnson Division, UOP mc, St Paul, MN p
1089
US EPA 1987 A Compendium of Superfund Field
Operations Methods EPA/540/p-87/00 I Office of
Emergency and Remedial Responses Washington,
DC
S
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APPENDIX A
Ge&is Forms
Form I Geolis® Borehole Logging Form
GEOLIS, Borehol. Logging Form
LOCATION 10
cuBIT 1E
u 1
LOU
hrrE /A k
U Pt1 3 METHOO SPB - S -518 -018- DJT - - NB FU.IO 41RV1 FTM B
OTHER._______________________ LOS5 NER
i n ALY11 a MP’J O P4TERVAL. (FTh4 B )
OVERY I FTM NA
TYP€ILAB UNO-08 .08P1 MO8.QEO.cHM.
SLOW F I I
COLP4II II II II 111
MA TYPE / LA8 UNO - O l E - CMP I MO E . €O - 0-lu.
UTHOLCOY NATt AL . PILL . U CERTAP4
&UN3 INTERVAL No
YES - NO OOBER%’W BIN- $HN -OOR- PTID. NA - O’fl- R
U1HOI.0 iC INTERVA l. NO.
lNaT 4T I TW READIN3.
U8•CI.O IC
INTERVAL 10 FT O IN9TRl.lu 4T a TYPE REAO IM3
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OCIOP MUP4.OSA
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8 MAX DIAM — P4
8 MAX AM — P4
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MATRIX - - . - -
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9
-------
APPENDIX A (Cont’d)
Geolis Forms
Form 2 Geolis® Well Construction Form
GEOUS 1 Well Construction Form 8h..t_ of
CATIOI4 iD *
P O. CT __________________ _________________
$ITE1P / 0 Afl E f.
START 0A12. _________________ It W ElEVATIONS O Th TO WATEI OA1 1 TINS
M EflON OATS ____________ rTft4
WELL. STA1% PIP. • OOL • P 404 eoi cr ___________ FT FTMCTOCI ______________
STATUS DATE CASIPdQ) P(TOC )
wEu,.’n . • - A.’TWLE S d - EN HOLE -P TED - P SE
C42540 S1NOI.E - 0lE - T .E RETIQN PUMP - P T . VALLI -CAP - NA
TOTAL CF ________ s 9 mEU. ________________
WEL .t E
WELL.
I — I 006N041 DIMCT t _____I INT W . TO______
T P -STh.L .QAL._ UO IAL 5-10-20 .40.IO._
CASINOEINTI T.2 f.1r.sOL..w c.sON.c . .i __________
CMIP40Z D MET ______20 W1E V?.L. _________To ________
r . FVC-UTN-L -5AL-_____ SO - DtA.E. O-I0.20-40.U0._
CAauIm•2 DIAMCT _____s IP41 VAL _______TO______
FY . C-Si L .GAL._ SO LU. 5--20-40 .SO_
ST P N CA$NS ______________ TjU OTJT CARPl3 _____________ P 1 1 14
S UT N _______________________
TO_______ PTM
PUC t T.P .04V cJ1P.ALl NON-i .2-s-on.l —
RAL TYIf I ____________ P4TERVAL. ______To______
TYPE 5 P4T y To_______
INC PAO( TYPE. INT A L. _________To _________
DIAMET . _____MI INT VAL To PTj14
rY,E. pyc.en .i - i . -pop .oi i _______________
SLOTS N . ELM. SLV - - OJT . 0114. _____________
sl.QT lI 5 -10 .20 -20 - 40 . SLOT
- UTMTIHTM J1OPW - ____________________________ I
ESTINAT WELl. hELD- __________ %PU DRAWDOWPE ________ VTN
WA1U 2AMPUNQ ShSTop NON - PP4P - WL TYPE. ____________________
SEA l INTERVAL_________ TO _________ TA I4TAl C 1H _________ ,Tjup p
NOTES _____________________________________________________
0P204 4-OLE DI1NST I _____P4 S4T VAL _______To______ 1114 IN
04AAOT E e P4T VAL _________TO P1 1 14
Sfl.TTNAPISI*IP 11 5 - P40 IM1• VM .. __________TO __________ TT 1 I 4 I N
NSIOE WELL TO ____________ P 1 1 W IN C *PSEJSAa ILL. O - S - 2114- N d
u.*PeE INT VAL TO P7 114 IN
OA 1UJNTERYAL _______To ,VUIOS TYPE. _________
WELL. OONSThUCITQP4 C €S
• INJe I N T IC • ________________________________________
— .s er •
TOT - W IN 1iIN ICS - IIC TO IN
- tflSC fl •
IN - TW en no -
TIC - IN IN -
PYTS 4T 01500.1204 by Roy E Wss r io QEOUS V.oen 20 DEC1924 61294
- PlOT SCALE — E Wi’
__________ sam Q OE
0
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I0
-------
CONCRETE F1LL.ED
GUARD POST
THIRD GUARD POST NOT SHOWN
APPENDIX B
Figures
FIGURE 1 Typical Bedrock Well Construction
TELESCOPING OR HINGED COVER
K PADLOCK
OVERSIZED CAP OR
UNDERSIZED PLUG
i.
2’X2’X4 CONCRETE
PAD
CONCRETE
CONCRETE FiLLED
GUARD POST
CASING
3.
GROUT
TOP OF
BEDROCK
BEDROCK
BoTrou OF
CASING
OPEN HOLE IN BEDROCK
NO CASING
DETERMINED IN FIELD
eorrou
OF WELl.
ii
-------
APPENDIX B (Cont’d)
Figures
FIGURE 2. Typical Overburden Well Constniction
2’ MINIMUM
TOP OF
SCREEN
BOTTOM OF
SCREEN
TELESCOPING OR
HINGED COVER
KEY PADLOCK
CONCRETE FILLED
GUARD POST
OVERSIZED CAP OR
UNDERSIZED PLUG
PROTECTWE CASING
PAD
CONCRETE
CONCRETE FILLED
GUARD POST
CASING
3.
DETERMINED IN FiELD
GROUT
BENTONITE
SEAL
______ — TOP OF
BENTON TE
TOP OF
SAND
SCREEN
DETERMINED IN FiELD
CAP OR PLUG
TOTAL. DEPTh
12
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MODEL 5400
GEOPROBE TM OPERATION
SOP#: 2050
DATE: 03/27/96
REV. # 0.0
1.0 SCOPE AND APPLICATION
The purpose of this standard operating procedure
(SOP) is to describe the collection of representative
soil, soil-gas, and groundwater samples using a Model
5400 Geoprobe sampling device Any deviations
from these procedures should be documented in the
sitelfield logbook and stated in project deliverables
Mention of trade names or commercial products does
not constitute U S Environmental Protection Agency
(U S EPA) endorsement or recommendation for use
2.0 METHOD SUMMARY
The Geoprobe sampling device is used to collect
soil, soil-gas and groundwater samples at specific
depths below ground surface (BGS) The Geoprobe TM
is hydrauhcaUy powered and is mounted in a
customized four-wheel drive vehicle The base of the
sampling device is positioned on the ground over the
sampling location and the vehicle is hydraulically
raised on the base As the weight of the vehicle is
transferred to the probe, the probe is pushed into the
ground A built-in hammer mechanism allows the
probe to be driven through dense materials
Maximum depth penetration under favorable
circumstances is about 50 feet Components of the
Model 5400 Geoprobe are shown in Figures 1
through 6 (Appendix A)
Soil samples are collected with a specially-designed
sample tube The sample tube is pushed and/or
vibrated to a specified depth (approximately one foot
above the intended sample mterval) The interior plug
of the sample tube is removed by inserting small-
diameter threaded rods The sample tube is then
dnven an additional foot to collect the samples The
probe sections and sample tube are then withdrawn
and the sample is extruded from the tube into sample
jars
Soil gas can be collected in two ways One method
involves withdrawing a sample directly from the
probe rods, after evacuating a sufficient volume of air
from the probe rods The other method involves
collecting a sample through tubing attached by an
adaptor to the bottom probe section Correctly used,
the latter method provides more reliable results
Slotted lengths of probe can be used to collect
groundwater samples if the probe rods can be driven
to the water table Groundwater samples are collected
using either a peristaltic pump or a small bailer
3.0 SAMPLE PRESERVATION,
CONTAINERS, HANDLING AND
STORAGE
Refer to specific ERT SOPs for procedures
appropriate to the matrix, parameters and sampling
objector
Applicable ERT SOPs include
ERT #20 12, Soil Sampling
ERT #2007, Groundwater Well Sampling
ERT #2042, Soil Gas Sampling
4.0 INTERFERENCES
POTENTIAL PROBLEMS
AND
A preliminary site survey should identify areas to be
avoided with the truck All underground utilities
should be located and avoided during sampling
Begin sampling activities with an adequate fuel
supply
Decontamination of sampling tubes, probe rods,
adaptors, non-expendable points and other equipment
that contacts the soil is necessary to prevent cross-
contamination of samples During sampling, the
bottom portion and outside of the sampling tubes can
be contaminated with soil from other depth intervals
-------
Care must be taken to prevent soil which does not
represent the sampled interval form being
incorporated into the sample Excess soil should be
carefully wiped from the outside surface of the
sampling tube and the bottom 3 inches of the sample
should be discarded before extruding the sample into
a sample jar
The amount of sample to be collected and the proper
sample container type (i e , glass, plastic), chemical
preservation, and storage requirements are dependent
upon the parameter(s) of interest Guidelines for the
containment, preservation, handling and storage of
soil-gas samples are described in ERT SOP #2042,
Soil-Gas Sampling
Obtaining sufficient volume of soil for multiple
analyses from o . sample location may present a
problem The Geoprobe” soil sampling system
recovers a limited volume of soil and it is not possible
to reenter the same hole and collect additional soil
When multiple analyses are to be performed on soil
samples collected with the Geoprobe TM , it is important
that the relative importance of the analyses be
identified Identifying the order of importance vill
ensure that the limited sample volume will be used for
the most crucial analyses
5.0 EQUIPMENT/APPARATUS
Sampling with the Geoprobe TM involves use of the
equipment listed below Some of the equipment is
used for all sample types, others are specific to soil
(S), soil gas (SG), or groundwater (GW) as noted
C Geoprobe tm sampling device
C Threaded probe rods (36”, 24’, and 12”
lengths)
C Drive Caps
C Pull Caps
C Rod Extractor
C Expendable Point Holders
C Expendable Drive Points
C Solid Drive Points
C Extension Rods
C Extension Rod Couplers
C Extension Rod Handle
C Hammer Anvil
C Hammer Latch
C Hammer Latch Tool
C Drill Steels
C Carbide-Tipped Drill Bit
C Mill-Slotted Well Point (GW)
C Threaded Drive Point (GW)
C Well Mini-Bailer (GW)
C Tubing Bottom Check Valve (OW)
C 3/8” 0 D Low Density Polyethylene Tubing
(OW, SO)
C Gas Sampling Adaptor and Cap (SO)
C Teflon Tape
C Neoprene “0” - Rings (SO)
C Vacuum System (mounted in vehicle) (SO)
C Piston Tip (5)
C Piston Rod (S)
C Piston Stop (5)
C Sample Tube (11 5” in length) (S)
C Vinyl Ends Caps CS)
C Sample Extruder (S)
C Extruder Pistons (Wooden Dowels) (5)
C Wire Brush
C Brush Adapters
C Cleaning Brush (Bottle)
6.0 REAGENTS
Decontamination solutions are specified in ERT
SOP #2006, Sampling Equipment Decontamination
7.0 PROCEDURES
Portions of the following sections have been
condensed from the Model 5400 Geoprobe TM
Operations Manual( I) Refer to this manual for more
detailed information concerning equipment
specifications, general maintenance, tools, throttle
control, clutch pump, GSK-58 Hammer, and trouble-
shooting A copy of this manual will be maintained
with the Geoprobe TM and on file in the Quality
Assurance (QA) office
7.1 Preparation
Determine extent of the sampling effort,
sample matrices to be collected, and types
and amounts of equipment and supplies
required to complete the sampling effort
2 Obtain and organize necessary sampling and
monitoring equipment
3 Decontaminate or pre-clean equipment, and
ensure that it is in working order
4 Perform a general site survey pnor to site
2
-------
entry in accordance with the site-specific
Health and Safely Plan
5 Use stakes or flagging to identify and mark
all sampling locations All sample locations
should be cleared for utilities prior to
sampling
7.2 Setup of Geoprobe TM
Back earner vehicle to probing location
2 Shifi the vehicle to park and shut off Ignition
3 Set parking brake and place chocks under
rear tires
4 Attach exhaust hoses so exhaust blows
downwind of the sampling location (this is
particularly important during soil gas
sampling)
5 Start engine using the remote ignition at the
Geoprobe operator position
6 Activate hydrauhc system by turning on the
Electrical Control Switch located on the
Geoprobe electrical control panel (Figure
I, Appendix A) When positioning the
probe, always use the SLOW speed The
SLOW speed switch is located on the
hydraulic control panel (Figure 2, Appendix
A)
Important: Check for clearance on
vehicle roof before folding Geoprobe 1M out
of the carrier vehicle.
7 Laterally extend the Geoprobe TM from the
vehicle as far as possible by pulling the
EXTEND control lever toward the back of
the vehicle while the GeoprobeN is
horizontal
8 Tistng the FOOT control, lower the Dernck
Slide so it is below cylinder (A) before
folding the Geoprobe” out of the carrier
vehicle (Figure 3, Appendix A) This will
ensure clearance at the roof of the vehicle
9 Use the FOLD, FOOT, and EX] END
controls to place Geoprobe TM to the exact
probing location Never begin probing m the
fully extended position
10 Using the FOLD control, adjust the long axis
of the probe,cylinder so that it is
perpendicular (visually) to the ground
surface
II Using the FOOT control, put the weight of
the vehicle on the probe unit Do not raise
the rear of the vehicle more than six inches
Important: Keep rear vehicle wheels on
the ground surface when transferring the
weight of the vehicle to the probe unit
Otherwise, vehicle may shift when
probing begins.
12 When the probe axis is vertical and the
weight of the vehicle is on the probe unit,
probing is ready to begin
7.3 Drilling Through
Pavement or Concrete
Surface
Position earner vehicle to drilling location
2 Fold unit out of earner vehicle
3 Deactivate hydraulics
4 Insert carbide-tipped drill bit into hammer
5 Activate HAMMER ROTATION control by
turning knob counter-clockwise (Figure 4,
Appendix A) This allows the dnll bit to
rotate when the HAMMER control is
pressed
6 Press down on HAMMER control to activate
counterclockwise rotation
7 Both the HAMMER control and the PROBE
control must be used when drilling through
the surface (Figure 4, Appendix A) Fully
depress the HAMMER control, and
incrementally lower the bit gradually into the
pavement by periodically depressing the
PROBE control
8 When the surface has been penetrated, turn
the HAMMER Control Valve knob
3
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clockwise to deactivate hammer rotation and
remove the drill bit from the HAMMER
Important: Be sure to deactivate the
rotary action before driving probe rods.
7.4 Probing
Position the earner vehicle to the desired
sampling location and set the vehicle parking
brake
2 Deploy Geoprobe Sampling Device
3 Make sure the hydraulic system is turned off
4 Lift up latch and insert hammer anvil into
hammer push latch back in (Figure 5,
Appendix A)
5 Thread the drive cap onto the male end of the
probe rod
6 Thread an expendable point holder onto the
other end of the first probe rod
7 Slip an expendable drive point into point
holder
8 Position the leading probe rod with
expendable drive point in the center of the
demck foot and directly below the hammer
anvil
Important: Positioning (he first probe rod
Is critical In order to drive the probe rod
vertically. Therefore, both the probe rod
and the probe cylinder shaft must be ii
the vertical position (Figure 6, Appendix
A).
9 To begin probing, activate the hydraulics and
push the PROBE Control downward When
advancing the first probe rod, always use the
SLOW speed Many times the probe rods
can be advanced using only the weight of the
carrier vehIcle When this is the case, only
the PROBE control is used
Important: When advancing rods, always
keep the probe rods parallel to (he probe
cylinder shaft (Figure 6, Appendix A)
This Is done by making minor
adjustments with the FOLD controL
FaI urc to keep probe rods parallel to
probe cylinder shaft may result in broken
rods and increased difficulty in achieving
desired sampling depth.
7.5 Probing - Percussion Hammer
The percussion hammer must be used in situations
where the weight of the vehicle is not sufficient to
advance the probe rods
I Make sure the Hammer Rotation Valve is
closed
2 Using the PROBE control to advance the rod,
press down the HAMMER control to allow
percussion to drive the rods (Figure 2,
Appendix A)
Important: Always keep static weight on
the probe rod or the rod will vibrate and
chatter while you are hammering, causing
rod threads to fracture and break.
3 Keep the hammer tight to the drive cap so the
rod will not vibrate
4 Periodically stop hammering and check if the
probe rods can be advanced by pushing only
5 Any time the downward progress of the
probe rods is refused, the demck foot may
lift off of the ground surface When this
happens, reduce pressure on the PROBE
control Do not allow the foot to rise more
than six inches off the ground or the vehicle’s
wheels may lift off the ground surface,
causing the vehicle to shift (Figure 6,
Appendix A)
6 As the demck foot is raised off the ground
surface, the probe cylinder may not be in a
perpendicular position If this happens, use
the FOLD control to correct the probe
cylinder position
7.6 Probing - Adding Rods
Standard probe rods are three feet in length
If the desired depth is more than three feet,
4
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another rod must be threaded onto the rod
that has been driven into the ground In
order to ensure a vacuum-tight seal (soil-gas
sampling), two wraps of teflon tape around
the thread is recommended
2 Using the PROBE control, raise the probe
cylinder as high as possible
Important: Always deactivate hydraulics
when adding rods.
3 Deactivate hydraulics
4 Unthread the dnve cap from the probe rod
that is in the ground
5 Wrap tef1c n tape around the threads
6 Thread the drive cap onto the male end of the
next probe rod to be used
7 After threading the drive cap onto the rod to
be added, thread the rod onto the probe rod
that has been driven into the ground Make
sure threads have been teflon taped
Continue probing
8 Continue these steps until the desired
sampling depth has been reached
7.7 Probing(PuIhng Rods
Once the probe rods have been driven to
depth, they can also be pulled using the
Geopmbe Machine
2 Turn off the hydraulics
3 Lift up latch and take the hammer anvil out
of the hammer
4 Replace the drive cap from the last probe rod
dnven with a pull cap
5 Lift up the hammer latch
6 Activate the hydraulics
7 Hold down on the PROBE control, and move
the probe cylinder down until the latch can
be closed over the pull cap
Important: If the latch will not close over
the pull cap, adjust the derrick assembly
by using the extend control. This wil
allow you to center the pull cap directly
below the hammer latch.
S Retract the probe rods by pulling up on the
PROBE control
Important: Do not raise the probe
cylinder all the way when pulling probe
rods or It will be impossible to detach a
rod (hat has been pulled out. However, it
is necessary to raise the probe cylinder far
enough to allow the next probe section to
be pulled.
9 After retracting the first probe rod, lower the
probe cylinder only slightly to ease the
pressure off of the hammer latch
10 Attach a clamping device to the base of the
rods where it meets the ground to prevent
rods from falling back into the hole
11 Raise the hammer latch
12 Hold the PROBE control up and raise the
probe cylinder as high as possible
13 Unthread the pull cap from the retracted rod
14 Unthread the retracted rod
15 Thread the pull cap onto the next rod that is
to be pulled
16 Continue these steps until all the rods are
retracted from the hole
17 Decontaminate all portions of the equipment
that have been in contact with the soil, soil
gas and groundwater
7.8 Soil-Gas Sampling
Interior Tubing
Without
Follow procedures outlined in Sections 71
through 7 6
2 Remove hammer anvil from hammer
5
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3 Thread on pull cap to end of probe rod
4 Retract rod approximately six inches
Retraction of the rod disengages expendable
drive point and allows for soil vapor to enter
rod
5 Unthread pull cap and replace it with a gas
sampling cap Cap is furnished with barbed
hose connector
Important: Shut engine ofT before taking
sample (exhaust fumes can cause faulty
sample data).
6 Turn vacuum pump on and allow vacuum to
build in tank
7 Open hne control valve For each rod used,
purge 300 liters of volume Example Three
rods used = 900 liters = 900 on gauge
8 After achieving sufficient purge volume,
close valve and allow sample line piessure
gauge to return to zero This returns sample
train to atmospheric pressure
9 The vapor sample can now be taken
Pinch hose near gas sampling cap to
prevent any outside vapors from
entering the rods
2 Insert synnge needle into center of
barbed hose connector and
withdraw vapor sample
10 To maintain suction at the sampling location,
penodically drain the vacuum tank
11 To remove rods, follow procedures outlined
in Section 7 7
7.9 Soil-Gas Sampling With Post-Run
Tubing (PRT)
Follow procedures outlined in Sections 7 1
through 7.6
2 Retract rod approximately six inches
Retraction of rod disengages expendable
drive point and allows for soil vapor to enter
rod
3 Remove pull cap from the end of the probe
rod
4 Position the Geoprobe TM to allow room to
work
5 Secure PRT Tubing Adapter with “0” - Ring
to selected tubing
6 Insert the adapter end of the tubing down the
inside diameter of the probe rods
7 Feed the tubing down the hole until it hits
bottom on the expendable point holder Cut
the tubing approximately two feet from the
top probe rod
8 Grasp excess tubing and apply some
downward pressure while turning it in a
counter-clockwise motion to engage the
adapter threads with the expendable point
holder
9 Pull up lightly on the tubing to test
engagement of threads
10 Connect the outer end of the tubing to silicon
tubing and vacuum hose (or other sampling
apparatus)
11 Follow the appropnate sampling procedure
(ERT SOP 2042, Soil Gas Sampling) to
collect a soil-gas sample
12 After collecting a sample, disconnect the
tubing from the vacuum hose or sampling
system
13 Pull up firmly on the tubing until it releases
from the adapter at the bottom of the hole
14 Extract the probe rods from the ground and
recover the expendable point holder with the
attached adapter
6
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15 Inspect the “O’-nng at the base of the
adapter to verify that proper sealing was
achieved during sampling The “O”-rmg
should be compressed
Note: If the “O”-ring is not compressed,
vapors from within the probe sections may
have been collected rather than vapors
from the intended sample interval.
7.10 Soil Sampling
Follow procedures outlined in Sections 7 1
through 7 6
2 Assemble soil-sampling tube
Thread piston rod into piston tip
2 Insert piston tip into sample tube,
seating piston tip into cutting edge
of sample tube
3 Thread drive head into threaded end
of sample tube
4 Thread piston stop pin into drive
head Stop pin should be tightened
with wrench so that it e\erlS
pressure against the piston rod
3 Attach assembled sampler onto leading probe
rod
4 Drive the sampler with the attached probe
rods to the top of the interval to be sampled
5 Move probe unit back from the top of the
probe rods to allow work room
6 Remove drive cap and lower extension rods
into inside diameter of probe rods using
couplers to join rods together
7 Attach extension rod handle to top extension
rod
8 Rotate extension rod handle clockwise until
the leading extension rod is threaded into the
piston stop in downhole
9 Continue to rotate extension rod handle
clockwise until reverse-threaded stop-pin has
disengaged from the drive head
10 Remove extension rods and attached stop-pin
from the probe rods
II Replace drive cap onto top probe rod
12 Mark thetop probe rod with a marker or tape
at the appropriate distance above the ground
surface (dependent on sample tube length)
13 Drive probe rods and sampler the designated
distance Be careful not to overdrive the
sampler which could compact the soil sample
in the tube, making it difficult to extrude
Important: Documentation of sample
location should include both surface and
subsurface identifiers. Example: Correct
Method - Sample Location S-6, 12.0’ -
13.0’. Incorrect Method - Samp
Location S-ti, 12.0’.
14 Retract probe rods from the hole and recover
the sample tube Inspect the sample tube to
confirm that a sample was recovered
15 Disassemble sampler Remove all parts
16 Position extruder rack on the foot of the
Geoprobe TM demck
17 Insert sample tube into e t ruder rack with the
cutting end up
18 Insert hammer anvil into hammer
19 Position the extruder piston (wood dowel)
and push sample out of the tube using the
PROBE control on the Geoprobe TM Collect
the sample as it is extruded in an appropriate
sample container
Caution: use care when performing th
task. Apply downward pressure
gradually. Use of excessive force couki
result In injury to operator or damage b
tools. Make sure proper diameter
extruder piston is used.
20 To remove rods follow procedures outlined
in Section 7 7
7
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7.11 Groundwater Sampling
Follow Sections 7 1 thorough 7 6 with the
following exception the Mill-Slotted Well
Rod with attached threaded drive point
should be the first section probed into the
ground Multiple sections of mill-slotted
well rods can be used to provide a greater
vertical section into which groundwater can
flow
2 Probe to a depth at which groundwater is
expected
3 Remove Drive Cap and insert an electric
water-level indicator to determine if water
has entered the slotted sections of probe rod
Refer to ERT SOP #2043, Water Level
Measurement, to determine water level
4 If water is not detected in the probe rods,
replace the drive cap and continue probing
Stop after each additional probe length and
determine if groundwater has entered the
slotted rods
5 After the probe rods have been driven into
the saturated zone, sufficient time should be
allowed for the water level in the probe rods
to stabilize
Note: It will be difficult if not impossible
to collect a groundwa r sample in aquifer
material small enough to pass through the
slots (<0.02 inch diameter).
6 Groundwater samples may be collecit d with
the 20-mL well Mini-Bailer or a pumping
device If samples are being collected for
volatile organic analysis (VOA), the 20-mL
Well Mini-Bailer should be used If samples
are being collected for a variety of analyses,
VOA samples should be collected first using
the bailer. Remaining samples can be
collected by pumping water to the surface
Withdrawing water with the pump is more
efficient than collecting water with the 20-
mL well Mirn.Bailer
Important: Documentation of sample
location should include both surface and
subsurface identifiers. Exam pie: Sample
Location GW-.6, 17’-21’ bgs, water level in
probe rods is 17 feet bgs, and the leading
section of probe rod is 21 feet bgs. Tl
water sample is from this zone, not from
17 feet bgs or 21 feet bgs.
7 Remove rods following procedures outlined
in Section 7 7
8.0 CALCULATIONS
Calculating Vapor Purge Volume for Soil-Gas
Sampling without Intenor Tubing
Volume of Air to be Purged (Liters)
Number of Rods in the Ground
Volume in Liters/l000 =
Vacuum Pump Instrument Gauge
= 300x
Reading on
9.0 QUALITY ASSURANCE!
QUALITY CONTROL
The following genera] QA procedures apply
All data must be documented on field data
sheets or within site logbooks
2 All instrumentation must be operated in
accordance with operating instructions as
supplied by the manufactiirer, unless
otherwise specified in the work plan
Equipment checkout and calibration
activities must occur prior to
sampling/operation and they must be
documen ted
10.0 DATA VALIDATION
This section is not applicable to this SOP
11.0 HEALTH AND SAFETY
When working with potentially hazardous materials,
follow U S EPA, OSI-JA and the REAC site specific
Health and Safety Plan The following is a list of
health and safety pi cautions which specifically apply
to Geoprobe TM operation
Always put vehicle in “park”, set emergency
the brake, and place chocks under the tires,
before engaging remote ignition
8
-------
2 If vehicle isparked onaloose or soft surface, 13 Always remove the hammer anvil or other
do not fully raise rear of vehicle with probe tool from the machine before folding the
foot, as vehicle may fall or move machine to the horizontal position
3 Always extend the probe unit out from the 14 The vehicle catalytic converter is hot and
vehicle and deploy the foot to clear vehicle may present a fire hazard when operating
roof line before folding the probe unit out over dry grass or combustibles
4 Operators should wear OSI-IA approved 15 Geoprobe TM operators must wear ear
steel-toed shoes and keep feet clear of probe protection OSI-IA approved ear protection
foot for sound levels exceeding 85 dba is
recommended
5 Operator should wear ANSI approved hard
hats 16 Locations of buried or underground utilities
and services must be known before starting
6 Only one person should operate the probe to drill or probe
machine nd the assemble or disassemble
probe roc , nd accessories 17 Shut down the hydraulic system and stop the
vehicle engine before attempting to clean or
7 Never place hands on top of a rod while it is service the equipment
under the machine
18 Exercise extreme caution when using
8 Turn off the hydraulic system while changing extruder pistons (wooden dowels) to extrude
rods, inserting the hammer anvil, or attaching soil from sample tubes Soil in the sample
accessories tube may be compacted to the point that the
extruder piston will break or shatter before it
9 Operator must stand on the control side of will push the sample out
the probe machine, clear of the probe foot
and mast, while operating controls 19 A thy chemical fire extinguisher (Type ABC)
should be kept with the vehicle at fl times
10 Wear safety glasses at all times during the
operation of this machine 12.0 REFERENCES
11 Never continue to exert downward pressure I Model 5400 Geoprob& Operations Manual
on the probe rods when the probe foot has Geoprobe TM Systems, Salina, Kansas July
risen six inches off the ground 27, 1990
12 Never exert enough downward pressure on a 2 Geoprobe TM Systems - 1995-96 Tools and
probe rod so as to lift the rear tires of the Equipment Catalog
vehicle off the ground
9
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APPENDIX A
Figures
FIGURE Etectncal Control Panel
10
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APPENDIX A (Cont’d)
Figures
FIGURE 2 Hydraulic Control Panel
8Iow Spu.d When
Po.ftIon G.oprob.
I I
-------
APPENDIX A (Cont’d)
Figures
FIGURE 3 Deployment of Geoprobe TM from Sampling Vehicle
(A) CYLPWER
DERR )(
SL1 E
12
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APPENDIX A (Cont’d)
Figures
FIGURE 4 Geoprobe TM Setup for Dnlling Through Concrete and Pavement
UVER
PROBE
0=
13
-------
APPENDIX A (Cont’d)
Figures
FIGURE 5 Inserting Hammer Anvil
LATcH
14
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APPENDIX A (Cont’d)
Figures
FIGURE 6. Probe Cylinder Shaft and Probe Rod - Parallel and Vertical
PROBE
CYLINDER
HAMMER
PROBE
CYLINDER
SHAFT
PROBE
ROD
Machine in Vertical
Operating Position
CARRER VEHICLE
15
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Un ed States
Environmental Protection
Agency
Office of Solid Waste and
Emergency Response
Wast sngton DC 20460
EPA
Compendium of ERT
Surface Water and
Sediment Sampling
Procedures
0 - -
EPA540P-91 ‘005
January 1991
-------
EPA/540(P-91/005
OSWER Directive 9360.4-03
January 1991
COMPENDIUM OF ERT SURFACE WATER AND
SEDIMENT SAMPLING
PROCEDURES
Sampling Equipment Decontamination
Surface Water Sampling
Sediment Sampling
Interim Final
Environmental Rcsponsc Tcam
Emergency Response Division
01 ( 1cc of Emergency and Remedial Response
U.S Environmental Protcciion Agency
Washington, DC 20460
Pnnted on Recycled Paper
-------
Notice
This document has been reviewed in accordance with U.S. Environmental Protection Agency policy and approved
for publication. Mention of trade names or commercial products does not constitute endorsement or
recommendation for use.
The policies and procedures established in this document are intended solely for the guidance of government
personnel, for use in the Superfund Removal Program. They are not intended, and cannot be relied upon, to
create any rights, substantive or procedural, enforceable by any party in litigation with the United States. The
Agency reserves the right to act at variance with these policies and procedures and to change them at any time
without public notice.
Depending on circumstances and needs, it may not be possible or appropriate to follow these procedures exactly
in all situations due to site conditions, equipment limitations, and limitations of the standard procedures.
Whenever these procedures cannot be followed as written, they may be used as general guidance with any and
all modifications fully documented in either QA Plans, Sampling Plans, or final reports of results.
Each Standard Operating Procedure in this compendium contains a discussion on quality assurance/quality
control (QAIQC). For more information on QA/QC objectives and requirements, refer to the Quality
Assurance/Quality Control Guidance for Removal Activities, OSWER directive 9360.4-01, EPA/540/G-90/004.
Questions, comments, and recommendations are welcomed regarding the Compendium of ERT Surface Water
and Sediment Sampling Procedures. Send remarks to:
Mr. William A. Coakley
Removal Program QA Coordinator
U.S. EPA - ERT
Raritan Depot - Building 18, MS-101
2890 Woodbridge Avenue
Edison, NJ 08837-3679
For additional copies of the Compendium of ERT Surface Water and Sediment Sampling Procedures, please
contact:
National Technical Information Service (NTIS)
U.S. Department of Commerce
5285 Port Royal Road
Springfield, VA 22161
(703) 487-4600
Ii
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Table of Contents
Section
10 SAMPUNG EQUIPMENT DECONTAMINATION: SOP #2006,
1.1 Scope and Application 1
1.2 Method Summary 1
1.3 Sample Preservation, Containers, Handling, and Storage 1
1.4 Interferences and Potential Problems 1
1.5 Equipment/Apparatus 1
1.6 Reagents 2
1.7 Procedures 2
1.7.1 Decontamination Methods 2
1.7.2 Field Sampling Equipment Cleaning Procedures 3
1.8 Calculations 3
1.9 Quality Assurance/Quality Control 3
1.10 Data Validation 4
1.11 Health and Safety 4
2.0 SURFACE WATER SAMPLING: SOP #2013
2.1 Scope and Application 5
2.2 Method Summary S
2.3 Sample Preservation, Containers, Handling, and Stcwage 5
2.4 Interferences and Potential Problems 5
2.5 Equipment/Apparatus 5
2.6 Reagents 6
2.7 Procedures 6
2.7.1 Preparation 6
2.7.2 Sampling Considerations 6
2.73 Sample Collection 6
2.8 Calculations 7
2.9 Quality Assurance/Quality Control 7
2.10 Data Validation 7
2.11 Health and Safety 8
3.0 SEDIMENT SAMPLING: SOP #2016
3.1 Scope and Application 9
3.2 Method Summary 9
3.3 Sample Preservation, Containers, Handling, and Storage 9
3.4 Interferences and Potential Problems 10
3.5 Equipment/Apparatus 10
3.6 Reagents 10
3.7 Procedures - 10
iii
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Section
3.7.1 Preparation 10
3.7.2 Sample Collection 10
3.8 Calculations 33
3.9 Quality Assurance/Quality Control 13
3.10 Data Validation 13
3.11 Health and Safety 14
APPENDIX A - Figures 15
REFERENCES 23
‘V
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Ust of Exhibits
Exhibit
Table 1: Recommended Solvent Rinse for Soluble Contaminants #2006 4
Figure 1: Keminerer Bottle #2013 16
Figure 2: Bacon Bomb Sampler #2013 17
Figure 3: Dip Sampler #2013 18
Figure 4: Sampling Auger #2016 9
Figure 5: Ekman Dredge #2016 20
Figure 6: Ponar Dredge #2016 21
Figure 7: Sampling Core Device #2016 22
V
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Acknowledgments
Preparation of this document was directed by William A. Coaldey, the Removal Program QA Coordinator of
the Environmental Response Team, Emergency Response Division. Additional support was provided under U.S.
EPA contract #63-03-34S2 and U.S. EPA contract #68-WO-0036.
vi
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1.0 SAMPLING EQUIPMENT DECONTAMINATION: SOP #2006
1.1 SCOPE AND APPLICATION
This Standard Operating Procedure (SOP) describes
methods used for preventing or reducing cross-
contamination, and provides general guidelines for
sampling equipment decontamination procedures at
a hazardous waste site. Preventing or minimizing
cross-contamination in sampled media and in
samples is important for preventing the introduction
of error into sampling results and for protecting the
health and safety of site personnel.
Removing or neutralizing contaminants that have
accumulated on sampling equipment ensures
protection of personnel from permeating substances,
reduces or eliminates transfer of contaminants to
clean areas, prevents the mixing of incompatible
substances, and minimizes the likelihood of sample
cross-contamination
1.2 METHOD SUMMARY
Contaminants can be physically removed from
equipment, or deactivated by sterilization or
disinfection. Gross contamination of cquipmcnt
requires physical decontamination, including
abrasive and non-abrasive methods. Thcsc includc
the usc of brushes, air and wtt blasting, and high.
pressure water cleaning, follosved by a wash/rincc
process using appropriate cleaning solutions. Usc
of a solvent rinse is required when org Inic
contamination is present
1.3 SAMPLE PRESERVATION,
CONTAINERS, HANDLING, AND
STORAGE
This SeCtiOn is nOt applicdl)le to hic SOP
1.4 INTERFERENCES AND
POTENTIAL PROBLEMS
The usc of disiilled/dcioni ed w,jtcr
corn monly available from comrnerci,il
vendors may he cccptabIe for
decontamination of sampling equipment
provided that it has been verified by
laboratory analysis to be analyte free.
• An untreated potable water supply is not
an acceptable substitute for tap water. Tap
water may be used from any municipal
water treatment system for mixing of
decontamination solutions.
• Acids and solvents utilized in the
decontamination sequence pose the health
and safety risks of inhalation or skin
contact, and raise shipping concerns of
permeation or degradation.
• The site s rk plan must address disposal
of the spent decontamination solutions.
• Several procedures can be established to
minimize contact with waste and the
potential for contamination. For example:
- Stress work practices that
minimi7c contact with hazardous
substances.
- Use remote sampling, handling,
and container-opening techniques
when appropriate.
- Cover monitoring and sampling
cquipmeril with protective material
to minimiic Contamination.
• Usc disposable outer garments
and disposable sampling
equipment when appropriate
1.5 EQUIPMENT/APPARATUS
• appropr l .IIe pcrson.il protectiw clothing
• non-phosphate detergent
• selected solvents
• long-handled hrLI hcs
• drop ckIih%/pl istIc .hicling
• trash wnt iiner
• paper t(Mvk
• galvaniicd uhs or hu ket
• tap water
-------
• distilled/deionized water
• metal/plastic containers for storage and
disposal of contaminated wash solutions
• pressurized sprayers for tap arid
deionized/distilled water
• sprayers for solvents
• trash bags
• aluminum foil
• safety glasses or splash shield
• emergency eyewash bottle
1.6 REAGENTS
There are no reagents used in this procedure aside
from the actual decontamination solutions and
solvents. In general, the following solvents are
utilized for decontamination purposes:
• 10% nitric acid
• acetone (pesticide rade) 2
• hexanc (pesticide grade) t2
• methanol
Only if sample is to be analyzed for trace metals.
(2) Only if sample is to be analyzed for organics.
1.7 PROCEDURES
As part of the health and safety plan, develop and
set up a decontamination plan before any personnel
or equipment enter the areas of potential exposure.
The equipment decontamination plan should
include:
• the number, location, and la ut of
decontamination stations
• which decontamination apparatus is needed
• the appropriate decontamination methods
• methods for disposal of contaminated
clothing, apparatus, and solutions
1.7.1 Decontamination Methods
All personnel, samples, and equipment leaving the
contaminated area of a site must be
decontaminated. Various decontamination methods
will either physically remove contaminants,
inactivate contaminants by disinfection or
sterilization, or do both
In many cases, gross contamination can be removed
by physical means. The physical decontamination
techniques appropriate for equipment
decontamination can be grouped into two
categories: abrasive methods and non-abrasive
methods.
Abrasive Cleaning Methods
Abrasive cleaning methods work by rubbing and
wearing away the top layer of the surface containing
the contaminant. The following abrasive methods
are available:
• Mechanical: Mechanical cleaning methods
use brushes of metal or nylon. The
amount and type of contaminants removed
will vary with the hardness of bristles,
length of brushing time, and degree of
brush contact.
• Air Blasting: Air blasting is used for
cleaning large equipment, such as
bulldozers, drilling rigs or auger bits. The
equipment used in air blast cleaning
employs compressed air to force abrasive
material through a nozzle at high velocities.
The distance between the nozzle and the
surface cleaned, as well as the pressure of
air, the time of application, and the angle
at which the abrasive strikes the surface,
determines cleaning efficiency. Air blasting
has several disadvantages: it is unable to
control the amount of material removed, it
can aerate contaminants, and it generates
large amounts of waste.
• Wet Blasting. Wet blast cleaning, also
used to clean large equipment, invelves usc
- of a suspended finc abrasive delivered by
comprcssed air to the contaminated area.
The amount of materials removed can he
carcfully controlled by using very fine
abrasives. This method gcneratcs a large
amount of waste
Non-Abrasive Cleaning Methods
Non-abrasive cleaning methods work by forcing the
contaminant off of a surface w h pressure In
general, less of tbc equipment surfacc is removed
using non-abrasive methods The following non-
abraswe methods arc available
2
-------
6. Rinse with distilled/deionized water.
• High-Pressure Water: This method
consists of a high-pressure pump, an
operator-controlled directional nozzle, and
a high pressure hose. Operating pressure
usually ranges from 340 to 680 atmospheres
(atm) which relates to flow rates of 20 to
140 liters per minute.
• Ultra-High-Pressure Water: This system
produces a pressurized water jet (from
1,000 to 4,000 atm). The ultra-high-
pressure spray removes tightly-adhered
surface film. The water velocity ranges
from 500 rn/sec (1,000 atm) to 900 rn/sec
(4,000 atm). Additives can enhance the
method. This method is not applicable for
hand-held sampling equipment.
Disinfection/Rinse Methods
• Disinfection: Disinfectants are a practical
means of inactivating infectious agents.
• Sterilization:
Standard
sterilization
methods in lve
heating the
equipment.
Sterilization
is
impractical
for large
equipment.
• Rinsing: Rinsing removes contaminants
through dilution, physical attraction, and
solubilization.
1.7.2 Field Sampling Equipment
Cleaning Procedures
Solvent rinses are not necessarily required when
organics are not a contaminant of concern and may
be eliminated from the sequence specified below.
Similarly, an acid rinse is not required if analysis
does not indude inorganics.
I Where applicable, follow physical removal
procedures specified in section 1.7.1.
2. Wash equipment with a non-phosphate
detergent solution.
3. Rinse with tap water.
4. Rinse with distilled/deionized Water.
5. Rinse with 10% nitric acid if the sample will be
analyzed for trace organics.
7. Use a solvent rinse (pesticide grade) if the
sample will be analyzed for organics.
8. Air dry the equipment completely.
9. Rinse again with distilled/deionized water.
Selection of the solvent for use in the
decontamination process is based on the
contaminants present at the site. Use of a solvent
is required when organic contamination is present
on-site. Typical solvents used for removal of
organic contaminants include acetone, hexane, or
water. An acid rinse step is required if metals are
present on-site. If a particular contaminant fraction
is not present at the site, the nine-step
decontamination procedure listed above may be
modified for site specificity. The decontamination
solvent used should not be among the contaminants
of concern at the site.
Table 1 lists solvent rinses which may be required
for elimination of particular chemicals. After çach
solvent rinse, the equipment should be air dried and
rinsed with distilled/deionized water.
Sampling equipment that requires the use of plastic
tubing should be disassembled and the tubing
replaced with clean tubing, before commencement
of sampling and between sampling locations.
1.8 CALCULATIONS
This section is not applicable to this SOP.
1.9 QUALITY ASSURANCE!
QUALITY CONTROL
One type of quality control sample specific to the
field decontamination process is the rinsate blank.
The rinsate blank provides information on the
effectiveness of the decontamination process
employed in the field. When used in conjunction
with field blanks and trip blanks, a rinsate blank can
detect contamination during sample handling,
storage and sample transportation to the laboratory.
3
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Table 1: Recommended Solvent Rinse for Soluble Contaminants
SOLVENT
SOLUBLE CONTAMINANTS
Water
• Low-chain hydrocarbons
• Inorganic compounds
• Salts
• Some organic acids and other polar compounds
Dilute Acids
• Basic (caustic) compounds
• Amines
• Hydrazines
Dilute Bases -- for example, detergent
and soap
• Metals
• Acidic compounds
• Phenol
• Thiols
• Some nitro and sulfonic compounds
Organic Solvents ’ - for example,
alcohols, ethers, ketones, arornatics,
straight-chain alkanes (e.g., hexane), and
common petroleum products (e g., fuel,
oil, kerosene)
• Nonpolar compounds (e.g., some organic compounds)
- WARNING: Some organic solvents can permcatc and/or degrade protective clothing.
A rinsatc blank consists of a sample of analyte-free
(i.c, deionized) water which is passed over and
through a field decontaminated sampling device and
placed in a clean sample container.
Rinsatc blanks should be run for all parameters of
intcrcst at a rate of 1 per 20 for each parameter,
even ii samples are not shipped that day. Rinsate
blanks are not required if dedicated sampling
cquipmcnt is used.
1.10 DATA VALIDATION
This scction is not applicable to this SOR
1.11 HEALTH AND SAFETY
Whcn working with potcntially hazardous materials,
follow U.S. EPA, OSHA and specific health and
safety procedures
Decontamination can pose hazards under certain
circumstances even though pcrformcd to protect
health and safety. Hazardous substances may be
incompatible with decontamination methods. For
example, the decontamination solution or solvent
may react with contaminants to produce heat,
explosion, or toxic products. Decontamination
methods may be incompatible with clothing or
equipment; some solvents can permeate or degrade
protective clothing. Also, decontamination solutions
and solvents may pose a direct health hazard to
workers through inhalation or skin contact, or if
they combust.
The decontamination solutions and solvents must be
determined to be compatible before use. Any
method that permeates, degrades, or damages
personal protective equipment should not be used.
If decontamination methods pose a direct health
hazard, measures should be taken to protect
personnel or the methods should be modified to
eliminate the hazard
4
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2.0 SURFACE WATER SAMPLING: SOP #2013
2.1 SCOPE AND APPLICATION
This Standard Operating Procedure (SOP) is
applicable to the collection of representative liquid
samples, both aqueous and nonaqueous from
streams, rivers, lakes, ponds, lagoons, and surface
impoundments. It includes samples collected from
depth, as well as samples collected from the surface.
2.2 METHOD SUMMARY
Sampling situations vary widely and therefore no
universal sampling procedure can be recommended.
However, sampling of both aqueous and non.
aqueous liquids from the above mentioned sources
is generally accomplished through the use of one of
the following samplers or techniques:
• Kemmerer bottle
• bacon bomb sampler
• dip sampler
• direct method
These sampling techniques will allow for the
collection of representative samples from the
majority of surface waters and impoundments
encountered.
5. Complete the chain of custody form.
6. Attach custody seals to the cooler prior to
shipment.
7. Decontaminate all sampling equipment prior to
the collection of additional samples.
2.4 INTERFERENCES AND
POTENTIAL PROBLEMS
There are two primary interferences or potential
problems with surface water sampling. These
include cross-contamination of samples and
improper sample collection.
Cross-contamination problems can be
eliminated or minimized through the use of
dedicated sampling equipment. If this is
not possible or practical, then
decontamination of sampling equipment is
necessazy. Refer to ERT SOP #2006,
Sampling Equipment Decontamination.
Improper sample collection can involve
using contaminated equipment, disturbance
of the stream or impoundment substrate,
and sampling in an obviously disturbed
area.
2.3 SAMPLE PRESERVATION,
CONTAINERS, HANDLING, AND
STORAGE
Once samples have been collected, follow these
procedures:
1. Transfer the sample(s) into suitable labeled
sample containers.
2. Preserve the sample if appropriate, or use pre-
preserved sample bottles.
3. Cap the container, put it in a Ziploc plastic bag
and place it on ice in a cooler.
4 Record all pertinent data in the site logbook
and on a field data sheet.
Following proper decontamination procedures and
minimizing disturbance of the sample site will
eliminate these problems.
2.5 EQUIPMENT/APPARATUS
Equipment needed for collection of surface water
samples includes
• Kemmerer bottles
• bacon bomb sampler
• dip sampler
• line and messengers
• sample bottle preservatives
• Ziploc bags
• ice
• cooler(s)
• chain of custody forms, field data sheets
5
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decontamination equipment
maps/plot plan
safety equipment
compass
tape measure
survey stakes, flags, or buoys and anchors
camera and film
logbook/waterproof pen
sample bottle labels
2.6 REAGENTS
Reagents will be utilized for preservation of samples
and for decontamination of sampling equipment.
The preservatives required are specified by the
analysis to be performed. Decontamination
solutions are specified in ERT Sop #2006,
Sampling Equipment Decontamination.
2.7 PROCEDURES
2.7.1 PreparatIon
1. Determine the extent of the sampling effort, the
sampling methods to be employed, and which
equipment and supplies are needed.
2. Obtain necessary sampling and monitoring
equipment.
3. Decontaminate or preclean equipment, and
ensure that it is in working order.
4. Prepare scheduling and coordinate with staff,
clients, and regulatory a gency, if appropriate.
5. Perform a general site survey prior to site entry
in accordance with the site-specific health and
safety plan.
6. Use stakes, flags, or buoys to identi1 i and mark
all sampling locations. If required, the
proposed locations may be adjusted based on
site access, property boundaries, and surface
obstructions.
2.7.2 Sampling Considerations
Representative Samples
In order to collect a representative, sample, the
hydrology and morphometrics (e.g., measurements
of volume, depth. etc.) of a stream or impoundment
should be determined prior lo sampling. This will
aid in determining the presence of phases or layers
in lagoons or impoundments, flow patterns in
streams, and appropriate sample locations and
depths.
Water quality data should be collected in
impoundments to determine if stratification is
present. Measurements of dissolved oxygen, pH,
and temperature can indicate if strata exist which
would effect analytical results. Measurements
should be collected at 1-meter intervals from the
substrate to the surface using an appropriate
instrument, such as a Hydrolab (or equivalent).
Water quality measurements such as dissolved
oxygen, pH, temperature, conductivity, and
oxidation-reduction potential can assist in the
interpretation of analytical data and the selection of
sampling sites and depths anytime surface water
samples are collected.
Generally, the deciding factors in the selection of a
sampling device for sampling liquids in streams,
rivers, lakes, ponds, lagoons, and surface
impoundments are:
• Will the sample be collected from the
shore or from a boat on the impoundment?
• What is the desired depth at which the
sample is to be collected?
• What is the overall depth and flow
direction of river or stream?
Sampler Composition
The appropriate sampling device must be of a
proper composition. Samplers constructed of glass,
stainless steel, PVC or PFTE (Teflon) should be
used based upon the analyses to be performed.
2.7.3 Sample Collection
Kemmerer Bottle
Kemmerer bottle (Figure 1, Appendix A) may be
used in most situations where site access is from a
boat or structure such as a bridge or pier, and
where samples at depth are required. Sampling
procedures are a follows
S
•
•
S
•
•
6
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1. Using a properly decontaminated Kemmerer
bottle, set the sampling device so that the
sampling end pieces are pulled away from the
sampling tube, allowing the substance to be
sampled to pass through this tube.
2. Lower the pre-set sampling device to the
predetermined depth. Avoid bottom
disturbance.
3. When the Kemmerer bottle is at the required
depth, send down the messenger, closing the
sampling device.
4. Retrieve the sampler and discharge the first 10
to 20 mL to dear any potential contamination
on the valve. Transfer the sample to the
appropriate sample container.
Bacon Bomb Sampler
A bacon bomb sampler (Figure 2, Appendix A) may
be used in similar situations to those outlined for
the Kemmerer bottle. Sampling procedures are as
follows:
1. Lower the bacon bomb sampler carefully to the
desired depth, allowing the line for the trigger
to remain slack at all times. When the desired
depth is reached, pull the trigger line until taut.
2. Release the trigger line and retrieve the
sampler.
3. Transfer the sample to the appropriate sample
container by pulling the trigger.
Dip Sampler
A dip sampler (Figure 3, Appendix A) is useful for
situations where a sample is to be recovered from
an outfall pipe or along a lagoon bank where direct
access is limited. The long handle on such a device
allows access from a discrete location. Sampling
procedures are as follows:
1. Assemble the device in accordance with the
manufacturer’s instructions.
2. Extend the device to the sample location and
collect the sample.
3. Retrieve the sampler and transfer the sample to
the appropriate sample container.
Direct Method
For streams, rivers, lakes, and other surface waters,
the direct method may be utilized to collect water
samples from the surface. This method is not to be
used for sampling lagoons or other impoundments
where contact with contaminants are a concern.
Using adequate protective clothing, access the
sampling station by appropriate means. For shallow
stream stations, collect the sample under the water
surface pointing the sample container upstream.
The container must be upstream of the collector.
Avoid disturbing the substrate. For lakes and other
impoundments, collect the sample under the water
surface avoiding surface debris and the boat wake.
When using the direct method, do not use pre-
preserved sample bottles as the collection method
may dilute the concentration of preservative
necessary for proper sample preservation.
2.8 CALCULATIONS
This section is not applicable to this SOP.
2.9 QUALITY ASSURANCE/
QUALITY CONTROL
There are no specific quality assurance activities
which apply to the implementation of these
procedures. However, the following general
QA/OC procedures apply:
• All data must be documented on field data
shects or within site logbooks.
• All instrumcntation must be operated in
accordance with operating instructions as
supplied by the manufacturer, unless
otherwise specified in the work plan.
Equipment checkout and calibration
activities must occur prior to
sampling/operation and they must be
documented.
2.10 DATA VALIDATION
This section is not applicable to this SOP.
7
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2.11 HEALTH AND SAFETY
When working with potentially hazardous materials,
follow U.S. EPA, OSHA and specific health and
safety procedures.
More specifically, when sampling lagoons or surface
impoundments containing known or suspected
hazardous substances, take adequate precautions.
The sampling team member collecting the sample
should not get too close to the edge of the
impoundment, where bank failure may cause him or
her to lose their balance. The person performing
the sampling should be on a lifeline and be wearing
adequate protective equipment. When conducting
sampling from a boat in an impoundment or flowing
waters, follow appropriate boating safety
procedures.
8
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3.0 SEDIMENT SAMPLING: SOP #2016
3.1 SCOPE AND APPLICATION
This Standard Operating Procedure (SOP) is
applicable to the collection of representative
sediment samples. Analysis of sediment may
determine whether concentrations of specific
contaminants exceed established threshold action
levels, or if the concentrations present a risk to
public health, welfare, or the environment.
The methodologies discussed in this procedure are
applicable to the sampling of sediment in both
flowing and standing water. They are generic in
nature and may be modified in whole or part to
meet the handling and analytical requirements of
the contaminants of concern, as well as the
constraints presented by the sampling area
However, if modifications occur, they should be
documented in the site logbook or report
summarizing field activities.
For the purposes of this procedure, sediments are
those mineral and organic materials situated
beneath an aqueous layer. The aqueous layer may
be either static, as in lakes, ponds, or other
impoundments or flowing, as in rivers and streams.
3.2 METHOD SUMMARY
Sediment samples may be recovered using a variety
of methods and equipment, depending on the depth
of the aqueous layer, the portion of the sediment
profile required (surface versus subsurface), the
type of sample required (disturbed versus
undisturbed) and the sediment type.
Sediment is collected from beneath an aqueous
layer either directly, using a hand-held device such
as a shovel, trowel, or auger, or indirectly using a
remotely activated device such as an Ekman or
Ponar dredge. Following collection, the sediment is
placed into a container constructed of inert
material, homogeni7cd, and transferred to the
appropriate sample containers The homogenization
procedure should not he used if sample analysis
includes volatile organics
3.3 SAMPLE PRESERVATION,
CONTAINERS, HANDLING, AND
STORAGE
• Chemical preservation of solids is generally
not recommended. Cooling is usually the
best approach, supplemented by the
appropriate holding time.
• Wide-mouth glass containers with Teflon-
lined caps are utilized for sediment
samples. The sample volume is a function
of the analytical requirements and will be
specified in the work plan.
• Transfer sediment from the sample
collection device to an appropriate sample
container using a stainless steel or plastic
lab spoon or equivalent. If composite
samples are collected, place the sediment
sample in a stainless steel, plastic or other
appropriate composition (e.g.: Teflon)
bucket, and mix thoroughly to obtain a
homogeneous sample representative of the
entire sampling interval. Then place the
sediment sample into labeled containers.
• Samples for volatile organic analysis must
be collected directly from the bucket,
before mixing the sample, to minimize loss
due to volatilization of contaminants.
• All sampling devices should be
decontaminated, then wrapped in
aluminum foil. The sampler should remain
in this wrapping until it is needed. Each
sampler should be used for only one
sample Dedicated samplers for sediment
samples may be impractical due to the
large number of sediment samples which
may be required and the cost of the
sampler. In this case, samplers should be
cleaned in the field using the
decontamination procedure described in
ERT SOP# 2006, Sampling Equipment
Decontamination
9
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3.4 INTERFERENCES AND
POTENTIAL PROBLEMS
Substrate particle size and organic content are
directly related to water velocity and flow
characteristics of a body of water. Contaminants
are more likely to be concentrated in sediments
typified by fme particle size and a high organic
content. This type of sediment is most likely to be
collected from depositional zones. In contrast,
coarse sediments with low organic content do not
typically concentrate pollutants and are found in
erosional zones. The selection of a sampling
location can, therefore, greatly influence the
analytical results.
3.5 EQUIPMENT/APPARATUS
Equipment needed for collection of sediment
samples includes:
• maps/plot plan
• safety equipment
• compass
• tape measure
• survey stakes, flags, or buoys and anchors
• camera and film
• stainless steel, plastic, or other appropriate
composition bucket
• 4-oz., 8-oz., and one-quart, wide-mouth jars
w/Tefion-lined lids
Ziploc plastic bags
logbook
sample jar labels
chain of custody forms, field data sheets
cooler(s)
ice
decontamination supplies/equipment
spade or shovel
spatula
scoop
trowel
bucket auger
• thin-walled auger
• extension rods
• T-handle
• sampling trier
• sediment coring device (tubes, points, drive
head, drop hammer, “eggshell check valve
devices, acetate cores)
• Ponar dredge
• Ekman dredge
• nylon rope
3.6 REAGENTS
Reagents are not used for preservation of sediment
samples. Decontamination solutions are specified in
ERT SOP #2006, Sampling Equipment
Decontamination.
3.7 PROCEDURES
3.7.1 Preparation
1. Determine the extent of the sampling effort,
the sampling methods to be employed, and
which equipment and supplies are required.
2. Obtain necessary sampling and monitoring
equipment.
3. Decontaminate or preclean equipment, and
ensure that it is in working order.
4. Prepare schedules, and coordinate with staff,
client, and regulatory agencies, if appropriate.
5. Perform a general site survey prior to site entry
in accordance with the site-specific health and
safety plan.
6. Use stakes, flags, or buoys to identify and mark
all sampling locations Specific site
characteristics, including flow regime, basin
morphometry, sediment characteristics, depth
of overlying aqueous layer, and extent and
nature of contaminant should be considered
when selecting sample location. If required,
the proposed locations may be adjusted based
on site access, property boundaries, and surface
obstructions
3.7.2 Sample Collection
Selection of a sampling device is most often
contingent upow (1) the depth of water at the
sampling location, and (2) the physical
characteristics of the medium to be sampled.
Sampling Surface Sediments with a
Trowel or Scoop From Beneath a
Shallow Aqueous Layer
Collection of surface sediment from beneath a
shallow aqueous layer can be accomplished with
•
•
•
•
•
•
•
•
•
•
10
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tools such as spades, shovels, and scoops Surface
material can be removed to the required depth;
then a stainless steel or plastic scoop should be used
to collect the sample.
This method can be used to collect consolidated
sediments but is limited somewhat by the depth of
the aqueous layer. Accurate, representative samples
can be collected with this procedure depending on
the care and precision demonstrated by the sample
team member. A stainless steel or plastic scoop or
lab spoon will suffice in most applications. Care
should be exercised to avoid the use of devices
plated with chrome or other materials. Plating is
particularly common with garden trowels.
Follow these procedures to collect sediment samples
with a scoop or trowel:
1. Using a precleaned stainless steel scoop or
trowel, remove the desired thickness of
sediment from the sampling area.
2. Transfer the sample into an appropriate sample
or homogenization container.
Sampling Surface Sediments with a Thin-
Wall Tube Auger From Beneath a Shallow
Aqueous Layer
This system consists of an auger, a series of
extension rods, and a “T” handle (see Figure 4,
Appendix A). The auger is driven into the sediment
and used to extract a core A sample of the core is
taken from the appropriate depth.
Use the following procedure to collect sediment
samples with a thin-walled auger:
1. Insert the auger into the material to be sampled
at a 0° to 450 angle from vertical. This
orientation minimizes spillage of the sample
from the sampler. Extraction of samples may
require tilting of the sampler.
2. Rotate the auger once or twice to cut a core of
material.
3. Slowly withdraw the auger, making sure that the
slot is facing upward.
4. An acetate core may be inserted into the auger
prior to sampling, if characteristics of the
sediments or body of water warrant. By using
this technique, an intact core can be extracted.
5. Transfer the sample into an appropriate sample
or homogenization container.
Sampling Deep Sediments with
Augers and Thin-Wall Tube Samplers
From Beneath a Shallow Aqueous Layer
This system uses an auger, a series of extension
rods, a 1’” handle, and a thin-wall tube sampler
(Figure 4, Appendix A). The auger bores a hole to
a desired sampling depth and then is withdrawn.
The auger tip is then replaced with a tube core
sampler, lowered down the borehole, and driven
into the sediment at the completion depth. The
core is then withdrawn and the sample collected.
This method can be used to collect consolidated
sediments, but is somewhat limited by the depth of
the aqueous layer.
Several augers are available which include bucket
and posthole augers. Bucket augers are bcitcr for
direct sample recovery, are fast, and provide a largc
volume of sample. Posthole augers have limited
utility for sample collection as they arc designed
more for their ability to cut through fibrous, rooted,
swampy areas.
Follow these procedures to collect sediment samples
with a hand auger:
1. Attach the auger bit to a drill extension rod,
then attach the “r handle to the drill extension
rod.
2. Clear the area to be sampled of any surface
debris.
3. Begin augering, periodically removing any
accumulated sediment Irom the auger bucket
4. After reaching the desired depth, slowly and
carefully remove the auger from boring.
(When sampling directly from the auger, collect
sample after the auger is removed from boring
and proceed to Step 10.)
5 Remove auger tip from drill rods and replace
with a precleaned thin-wdll tube sampler
Install proper cutting tip.
6. Carefully lower tube sampler down borehole
Gradually Iorcc tube sampler into sediment
11
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Care should be taken to avoid scraping the
borehole sides. Also, avoid hammering of the
drill rods to facilitate coring, since the
vibrations may cause the boring walls to
collapse.
7. Remove tube sampler and unscrew drill rods.
8. Remove cutting tip and remove core from
device.
9. Discard top of core (approximately 1 inch), as
this represents material collected by the tube
sampler before penetration of the layer of
concern.
10. Transfer sample into an appropriate sample or
homogenization container.
Sampling Surface Sediments From
Beneath a Deep Aqueous Layer with
an Ekman or Ponar Dredge
This technique consists of lowering a sampling
device to the sediment by use of a rope, cable, or
extended handle. The mechanism is triggered, and
the device entraps sediment in spring-loaded jaws,
or within lever-operated jaws.
Follow these procedures for collecting sediment
with an Ekman dredge (Figure 5, Appendix A):
1. Thread a sturdy nylon or stainless steel cable
through the bracket, or secure the extended
handle to the bracket with machine bolts.
2. Attach springs to both sides. Arrange the
Ekman dredge sampler so that the jaws are in
the open position and trip cables are positioned
over the release studs
3. Lower the sampler to a point just above the
sediment surface.
4. Drop the sampler sharply onto the sediment.
5. Trigger the jaw release mechanism by lowering
a messenger down the line, or by depressing the
button on the upper end of the extended
handle
6. Raisc the sampler and slowly decant any free
liquid through the top of the sampler. Be
careful to retain line sediments.
7. Open the dredge and transfer the sediment into
a stainless steel or plastic bucket. Continue to
collect additional sediment until sufficient
material has been secured. Thoroughly mix
sediment to obtain a homogeneous sample, and
then transfer to the appropriate sample
container.
8. Samples for volatile organic analysis must be
collected directly from the bucket before mixing
the sample to minimize volatilization of
contaminants.
Follow these procedures for collecting sediment
with a Ponar dredge (Figure 6, Appendix A):
1. Attach a sturdy nylon or steel cable to the hook
provided on top of the dredge.
2. Arrange the Ponar dredge sampler in the open
position, setting the trip bar so the sampler
remains open when lifted from the top.
3. Slowly lower the sampler to a point just above
the sediment.
4. Drop the sampler sharply into the sediment,
then pull sharply up on the line, thus releasing
the trip bar and dosing the dredge.
5. Raise the sampler to the surface and slowly
decant any free liquid through the screens on
top of the dredge. Be careful to retain fine
sediments.
6. Open the dredge and transfer the sediment to
a stainless steel or plastic bucket. Continue to
collect additional sediment until sufficient
material has been gained. Thoroughly mix
sediment to obtain a homogeneous sample, and
then transfer to the appropriate sample
container.
7. Samples for volatile organic analysis must be
collected directly from the bucket before mixing
the sample to minimize volatilization of
contaminants.
Sampling Subsurface Sediments From
Beneath a Deep Aqueous Layer with a
Sample Coring Device
Follow these procedures when using a sample
coring device (Figure 7, Appendix A) to collect
12
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subsurface sediments. It consists of a coring device,
handle, and acetate core utilized in the following
procedure:
1. Assemble the coring device by inserting the
acetate core into the sampling tube.
2. Insert the “eggshell 0 check valve mechanisms
into the tip of the sampling tube with the
convex surface positioned inside the acetate
core.
3. Screw the coring point onto the tip of the
sampling tube.
4. Screw the handle onto the upper end of the
sampling tube and add extension rods as
needed.
5. Place the sampler in a perpendicular position
on the material to be sampled.
6. This sampler may be used with either a drive
hammer for firm consolidated sediments, or a
“T” handle for soft sediments. If the “T” handle
is used, place downward pressure on the device
until the desired depth is reached. Rotate the
sampler to shear off the core of the bottom,
retrieve the device and proceed to Step 15.
7. If the drive hammer is selected, insert the
tapered handle (drive head) of the drive
hammer through the drive head.
8. With left hand holding the tube, drive the
sampler into the material to the desired depth
Do not drive the tube furthcr than the tip of
the hammer’s guide.
9. Record the length of the tube that pcnetrated
the sample material, and the numbcr of blows
required to obtain this depth.
10. Remove the drive hammer and fit the keyhole-
like opening on the flat side of the hammer
onto the drivc head In this position, the
hammer servcs as a handle for the sampler.
1]. Rotate the sampler at least two revolutions to
shear off the sample at the bottom.
12. Lower the samplcr handlc (hammcr) until it
just clears the two car-like protrusions on the
drive head, and rotate about 900
13. Withdraw the sampler by puffing the handle
(hammer) upwards and dislodging the hammer
from the sampler.
14. Unscrew the coring point and remove the
“eggshell’ check valve.
15. Slide the acetate core out of the sampler tube.
The acetate core may be capped at both ends.
The sample may be used in this fashion, or the
contents transferred to a stainless steel or
plastic bucket and mixed thoroughly to obtain
a homogeneous sample representative of the
entire sampling interval.
16. Samples for volatile organic analysis must be
collected directly from the bucket before mixing
the sample to minimize volatilization of
contaminants.
3.8 CALCULATIONS
This section is not applicable to this SOP.
3.9 QUALflY ASSURANCE/
QUALITY CONTROL
There are no specific quality assurance activities
which apply to the implementation of these
procedures. However, the following QA/OC
procedures apply:
1. All data must be documented on field data
sheets or within site logbooks.
2. All instrumentation must be operated in
accordance with operating instructions as
supplied by the manufacturer, unless otherwise
specified in the work plan. Equipment
checkout and calibration activities must occur
prior to sampling/operation, and they must be
documented.
3.10 DATA VALIDATION
This section is not applicable to this SOP.
13
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3.11 HEALTH AND SAFETY
When working with potentially hazardous materials
follow U.S. EPA, OSIIA and specific health and
safety procedures.
More specifically, when sampling sediment from
bodies of water containing known or suspected
hazardous substances, adequate precautions must be
taken to ensure the sampler’s safety. The team
member collecting the sample should not get too
close to the edge of the water, where bank failure
may cause him or her to lose their balance. To
prevent this, the person performing the sampling
should be on a lifeline, and be wearing adequate
protective equipment. If sampling from a vessel is
necessary, implement appropriate protective
measures.
14
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APPENDIX A
Figures
15
-------
9OTTO .4 DRAIN
Figure 1: Kemmerer Bottle
SOP #2013
MESSENGER
CABLE
TRIP HEAD
CHAIN
CENTER ROD
STOPPER
116
-------
Figure 2: Bacon Bomb Sampler
SOP #2013
17
-------
Figure 3: Dip Sampler
SOP #2013
18
-------
Figure 4: Sampling Auger
SOP #2016
TUBE
AUGER
BUCKET
AUGER
II
II
‘9
-------
Figure 5: Ekman Dredge
SOP #2016
20
-------
Figure 6: Ponar Dredge
SOP #2016
21
-------
Figure 7: Sample Coring Device
SOP #2016
PLASflC
TUBE
8
BRASS
PLASI1C
22
-------
References
Barth, D.S. and B.J. Mason. 1984. Soil Sampling Quality Assurance User’s Guide. EPA-600/4-84/043.
de Vera, E.R., B.P. Simmons, R.D. Stephen, and D.L. Storm. 1980. Samplers and Sampling Procedures for
Hazardous Waste Streams. EPA/600j2-80/018.
Mason, BJ. 1983. Preparation of Soil Sampling Protocol: Technique and Strategies. EPA-600/4-83/020.
National Institute for Safety and Health. October, 1985. Occupational Safety and Health Guidance Manual for
Hazardous Waste Site Activities. [ Alternate title: Guidance Manual for Hazardous Waste Sites]
New Jersey Department of Environmental Protection, Division of Hazardous Site Mitigation. 1988. Field
Sampling Procedures Manual.
U.S. EPA. 1984. Characterization of Hazardous Waste Sites - A Methods Manual: Volume II. Available
Sampling Methods, Second Edition. EPA/600/4-84/076.
U.S. EPA Region IV, Environmental Services Division. April 1, 1986. Engineering Support Branch Standard
Operating Procedures and Quality Assurance Manual. Athens, Georgia.
U.S. EPA, OSWER/Remedial Planning and Response Branch. December 1, 1987. Compendium of Superfund
Field Operation Methods. EPA/540/P-87/OO1.
U.S. Geological Survey. 1977. National Handbook of Recommended Methods for Water Data Acquisition.
Office of Water Data Coordination. Reston, Virginia. (Chapter updates available).
23 US G rr ontPüiU O flce 1B9 — 548-1BU4 58O
-------
United S Center for Environmental Research
Environrnei iaI Protection Information BULK RATE
Agency Cincinnati OH 45268-1072 POSTAGE & FEES PAID
EPA
PERMIT No G-35
Oflucial Business
Penalty loi Private Use. $300
EPA 540 P-9 11005
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United States Office of Sold Waste and EPA 540 P-91 0ü8
Environmental Protection Emergency Response January 1991
Agency Washington DC 20460
&EPA Compendium of ERT
Waste Sampling
Procedures
. 1
-------
EPA/5401P-91/008
OSWER Directive 9360.4-07
January 1991
COMPENDIUM OF ERT WASTE
SAMPLING PROCEDURES
Sampling Equipment Decontamination
Drum Sampling
Tank Sampling
Chip, Wipe, and Sweep Sampling
Waste Pile Sampling
Interim Final
Environmental Response Team
Emergency Response Division
Office of Emergency and Remedial Response
U.S. Environmental Protection Agency
Washington, DC 20460
Printed on Recycled Paper
-------
Notice
This document has been reviewed in accordance with U.S. Environmental Protection Agency policy and approved
for publication. Mention of trade names or commercial products does not constitute endorsement or
recommendation for use.
The policies and procedures established in this document are intended solely for the guidance of government
personnel, for use in the Superfund Removal Program. They are not intended, and cannot be relied upon, to
create any rights, substantive or procedural, enforceable by any party in litigation with the United States. The
Agency reserves the right to act at variance with these policies and procedures and to change them at any time
without public notice.
Depending on circumstances and needs, it may not be possible or appropriate to follow these procedures exactly
in all situations due to site conditions, equipment limitations, and limitations of the standard procedures.
Whenever these procedures cannot be followed as written, they may be used as general guidance with any and
all modifications fully documented in either QA Plans, Sampling Plans, or final reports of results.
Each Standard Operating Procedure in this compendium contains a discussion on quality assurance/quality
control (QA/QC). For more information on QA/QC objectives and requirements, refer to the Quality
Assurance/Quality Control Guidance for Removal Activities, OSWER directive 93604-01, EPA/540/G-90/004.
Questions, comments, and recommendations are welcomed regarding the Compendium of ERT Waste Sampling
Procedures. Send remarks to:
Mr William A. Coakley
Removal Program QA Coordinator
U.S. EPA - ERT
Raritan Depot - Building 18, MS-101
2890 Woodbridge Avenue
Edison, NJ 08837-3679
For additional copies of the Compendium of ERT Waste Sampling Procedures, please contact:
National Technical Information Service (NTIS)
U.S. Department of Commerce
5285 Port Royal Road
Springfield, VA 22161
(703) 487-4600
Li
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Table of Contents
Section
1.0 SAMPLING EQUIPMENT DECONTAMINATION: SOP #2006
1.1 Scope and Application 1
1.2 Method Summary 1
1.3 Sample Preservation, Containers, Handling, and Storage 1
1.4 Interferences and Potential Problems 1
1.5 Equipment/Apparatus 1
1.6 Reagents 2
1.7 Procedures 2
1.7.1 Decontamination Methods 2
1.7.2 Field Sampling Equipment Cleaning Procedures 3
1.8 Calculations 3
1.9 Quality Assurance/Quality Control 3
1.10 Data Validation 4
1.11 Health and Safety 4
2.0 DRUM SAMPLING: SOP #2009
2.1 Scope and Application 5
2.2 Method Summary 5
2.3 Sample Preservation, Containers, Handling, and Storage 5
2.4 Interferences and Potential Problems 5
2.5 Equipment/Apparatus 6
2.5.1 Bung Wrench 6
2.5.2 Drum Deheader 6
2.5.3 Hand Pick, Pickax; and Hand Spike 6
2.5.4 Backhoe Spike 6
2.5.5 Hydraulic Drum Opener 6
2.5.6 Pneumatic Devices 6
2.6 Reagents 6
2.7 Procedures 7
2.7.1 Preparation 7
2.7.2 Drum Inspection 7
2.73 Drum Staging
2.7.4 Drum Opening 8
2.7.5 Drum Sampling 9
2.8 Calculations 11
2.9 Quality Assurance/Quality Control 11
2.10 Data Validation 11
2.11 Health and Safety 11
‘It
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Section
3.0 TANK SAMPLING: SOP #2010
3.1 Scope and Application 13
3.2 Method Summary 13
3.3 Sample Preservation, Containers, Handling, and Storage 13
34 Interferences and Potential Problems 13
3.5 Equipment/Apparatus 14
3.6 Reagents 14
3.7 Procedures 14
3.7.1 Preparation 14
3.7 2 Preliminary Inspection 14
3.7.3 Sampling Procedures 15
3.74 Sampling Devices 15
3.8 Calculations 18
3.9 Quality Assurance/Quality Control 18
3.10 Data Validation 18
3.11 Health and Safety 18
4.0 CHIP, WIPE, AND SWEEP SAMPLING: SOP #2011
4.1 Scope and Application 21
4.2 Method Summary 21
4.3 Sample Preservation, Containers, Handling, and Storage 21
4.4 Interferences and Potential Problems 21
4.5 Equipment/Apparatus 21
4.6 Reagents 22
4.7 Procedures 22
4.7.1 Preparation 22
4.7.2 Chip Sample Collection 22
4.7.3 Wipe Sample Collection 22
4.7.4 Sweep Sample Collection 23
4.8 Calculations 23
4.9 Quality Assurance/Quality Control 23
4.10 Data Validation 24
4.11 Health and Safety 24
5.0 WASTE PILE SAMPLING: SOP #2017
5.1 Scope and Application 25
5.2 Method Summary 25
5.3 Sample Preservation, Containers, Handling, and Storage 25
5.4 Interferences and Potential Problems 2.5
5.5 Equipment/Apparatus 26
5.6 Reagents 26
iv
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Section
5.7 Procedures
5.7.1 Preparation
5.7.2 Sample Collection
5.8 Calculations 29
5.9 Quality Assurance/Quality Control 29
5.10 Data Validation 29
5.11 Health and Safety 29
APPENDIX A - Drum Data Sheet Form 31
APPENDIX B . Figures 35
APPENDIX C Calculations 51
REFERENCES
V
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List of Exhibits
Exhibit
Table 1: Recommended Solvent Rinse for Soluble Contaminants #2006 4
Drum Data Sheet Form #2009 33
Figure 1: Univeral Bung Wrench #2009 36
Figure 2: Drum Deheader #2009 37
Figure 3: Hand Pick, Pickaxe, and Hand Spike #2009 38
Figure 4: Backhoe Spike #2009 39
Figure 5: Hydraulic Drum Opener #2009 40
Figure 6: Pneumatic Bung Remover #2009 41
Figure 7: Glass Thief #2009 42
Figure 8: COLIWASA #2009 43
Figure 9: Bacon Bomb Sampler #2010 44
Figure 10: Sludge Judge #2010 45
Figure 11: Subsurface Grab Sampler #2010 46
Figure 12: Bailer #2010 47
Figurc. 13: Sampling Augers #2017 48
Figure 14: Sampling Trier #2017 49
Figure 15: Grain Sampler #2017 50
Calculation Sheet: Various Volume Calculations #2010 52
•vl
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Acknowledgments
Preparation of this document was directed by William A. Coaldey, the Removal Program QA Coordinator of
the Environmental Response Team, Emergency Response Division. Additional support was provided under U.S.
EPA contract #68-03-3482 and U.S. EPA contract #68-WO-0036.
vu
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1.0 SAMPLING EQUIPMENT DECONTAMINATION: SOP #2006
1.1 SCOPE AND APPLICATION
This Standard Operating Procedure (SOP) describes
methods used for preventing or reducing cross-
contamination, and provides general guidelines for
sampling equipment decontamination procedures at
a hazardous waste site. Preventing or minimizing
cross-contamination in sampled media and in
samples is important for preventing the introduction
of error into sampling results and for protecting the
health and safety of site personnel.
Removing or neutralizing contaminants that have
accumulated on sampling equipment ensures
protection of personnel from permeating substances,
reduces or eliminates transfer of contaminants to
clean areas, prevents the mixing of incompatible
substances, and minimizes the likelihood of sample
cross-contamination.
1.2 METHOD SUMMARY
Contaminants can be physically removed from
equipment, or deactivated by sterilization or
disinfection. Gross contamination of equipment
requires physical decontamination, including
abrasive and non-abrasive methods. These includc
the use of brushes, air and vet blasting, and high-
pressure water cleaning, folIo ved by a wash/rinse
process using appropriate cleaning solutions Use
of a solvent rinse is required when organic
contamination is present.
1.3 SAMPLE PRESERVATION,
CONTAINERS, HANDLING, AND
STORAGE
This section is not applicable to this SOP.
1.4 INTERFERENCES AND
POTENTIAL PROBLEMS
• The use of distilled/deionized water
commonly available from commercial
vendors may be acceptable for
decontamination of sampling equipment
provided that it has been verified by
laboratory analysis to be analyte free.
• An untreated potable water supply is not
an acceptable substitute for tap water. Tap
water may be used from any municipal
water treatment system for mixing of
decontamination solutions.
• Acids and solvents utilized in the
decontamination sequence pose the health
and safety risks of inhalation or skin
contact, and raise shipping concerns of
permeation or degradation.
• The site rk plan must address disposal
of the spent decontamination solutions.
• Several procedures can be established to
minimize contact with waste and the
potential for contamination. For example:
- Stress work practices that
minimize contact with hazardous
substances.
• Use remote sampling, handling,
and container-opening techniques
when appropriate.
- Cover monitoring and sampling
equipment with protective material
to minimize contamination.
- Use disposable outer garments
and disposable sampling
equipment when appropriate.
1.5 EQUIPMENT/APPARATUS
• appropriate personal protective clothing
• non-phosphate detergent
• selected solvents
• long-handled brushes
• drop cloths/plastic sheeting
• trash container
• paper to vels
• galvanized tubs or buckets
• tap water
1
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• distilled/deionized water
• metal/plastic containers for storage and
disposal of contaminated wash solutions
• pressurized sprayers (or tap and
deionized/distilled water
• sprayers for solvents
• trash bags
• aluminum foil
• safety glasses or splash shield
• emergency eyewash bottle
1.6 REAGENTS
There are no reagents used in this procedure aside
from the actual decontamination solutions and
solvents. In general, the foIk ving solvents are
utilized for decontamination purposes:
• 10% nitric acid ’
• acetone (pesticide grade) t2
• hexane (pesticide grade) 2
• meLhanol
(1) Only if sample is to be analyzed for trace metals.
(2) Only if sample is to be analyzed for organics.
1.7 PROCEDURES
As part of the health and safety plan, develop and
set up a decontamination plan before any personnel
or equipment enter the areas of potential exposure.
The equipment decontamination plan should
include:
• the number, location, and layvut of
decontamination stations
• which decontamination apparatus is needed
• the appropriate decontamination methods
• methods for disposal of contaminated
clothing, apparatus, and solutions
1.7.1 DecontamInation Methods
All personnel, samples, and equipment leaving the
contaminated area of a site must be
decontaminated. Various decontamination methods
will either physically remove contaminants,
inactivate contaminants by disinfection or
sterilization, or do both.
In many cases, gross contamination can be removed
by physical means. The physical decontamination
techniques appropriate for equipment
decontamination can be grouped into t
categories: abrasive methods and non-abrasive
methods.
Abrasive Cleaning Methods
Abrasive cleaning methods v vrk by rubbing and
wearing away the top layer of the surface containing
the contaminant. The following abrasive methods
are available:
• Mechanical: Mechanical cleaning methods
use brushes of metal or nylon. The
amount and type of contaminants removed
will vary with the hardness of bristles,
length of brushing time, and degree of
brush contact.
• Air Blasting: Aix blasting is used for
cleaning large equipment, such as
bulldozers, drilling rigs or auger bits. The
equipment used in air blast cleaning
empk ’s compressed air to force abrasive
material through a nozzle at high velocities.
The distance between the nozzle and the
surface cleaned, as vvell as the pressure of
air, the time of application, and the angle
at which the abrasive strikes the surface,
determines deaning efficiency. Air blasting
has several disadvantages: it is unable to
control the amount of material removed, it
can aerate contaminants, and it generates
large amounts of waste.
• Wet Blasting: Wet blast cleaning, also
used to clean large equipment, Inwilves use
of a suspended fine abrasive delivered by
compressed air to the contaminated area.
The amount of materials removed can be
carefully controlled by using wry fine
abrasives. This method generates a large
amount of waste.
Non-Abrasive Cleaning Methods
Non-abrasive deaning methods v vrk by forcing the
contaminant off of a surface with pressure. In
genera], less of the equipment surface is removed
using non-abrasive methods. The following non-
abrasive methods are available:
2
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• High-Pressure Water: This method
consists of a high-pressure pump, an
operator-controlled directional nozzle, and
a high pressure hose. Operating pressure
usually ranges from 340 to 680 atmospheres
(atm) which relates to flow rates of 20 to
140 liters per minute.
• Ultra-High-Pressure Water: This system
produces a pressurized water jet (from
] 000 to 4,000 atm). The ultra-high-
pressure spray remo s tightly-adhered
surface film. The water ulocity ranges
from 500 rn/sec (1,000 atm) to 900 rn/sec
(4,000 atm). Additi s can enhance the
method. This method is not applicable for
hand-held sampling equipment.
Disinfection/Rinse Methods
• Disinfection: Disinfectants are a practical
means of inactivating infectious agents.
• Sterilization:
methods rnw)h
Sterilization is
equipment.
• Rinsing: Rinsing removes contaminants
through dilution, physical attraction, and
solubilization.
1.7.2 Field Sampling Equipment
Cleaning Procedures
Solvent rinses are not necessarily required when
organics are not a contaminant of concern and may
be eliminated from the sequence specified below
Similarly, an acid rinse is not required if analysis
does not include inorganics.
L Where applicable, follow physical remo l
procedures specified in section 1.7.1.
2. Wash equipment with a non-phosphate
detergent solution.
3. Rinse with tap water.
4. Rinse with distilled/deionized water.
S. Rinse with 10% nitric acid if the sample will be
analyzed for trace organics.
6. Rinse with distilled/deionized water.
7. Use a solvent rinse (pesticide grade) if the
sample will be analyzed for organics.
8. Air dry the equipment completely.
9. Rinse again with distilled/deionized water.
Selection of the solvent for use in the
decontamination process is based on the
contaminants present at the site. Use of a solvent
is required when organic contamination is present
on-site. Typical solvents used for removal of
organic contaminants include acetone, hexane, or
water. An acid rinse step is required if metals are
present on-site If a particular contaminant fraction
is not present at the site, the nine-step
decontamination procedure listed above may be
modified for site specificity. The decontamination
solvent used should not be among the contaminants
of concern at the site.
Table 1 on page 4 lists solvent rinses which may be
required for elimination of particular chemicals.
After each solvent rinse, the equipment should be
air dried and rinsed with distilled/deionized water.
Sampling equipment that requires the use of plastic
tubing should be disassembled and the tubing
replaced with clean tubing, before commencement
of sampling and bet’ veen sampling locations.
1.9 QUALITY ASSURANCE/
QUALITY CONTROL
One type of quality control sample specific to the
field decontamination process is the rinsate blank.
The rinsate blank provides information on the
effectiveness of the decontamination process
emplo vd in the field. When used in conjunction
with field blanks and trip blanks, a rinsate blank can
detect contamination during sample handling,
storage and sample transportation to the laboratory.
Standard
heating the
impractical
sterilization
equipment.
for large
1.8 CALCULATIONS
This section is not applicable to this SOP.
3
-------
Table 1: Recommended Solvent Rinse for Soluble Contaminants
SOLVENT
SOLUBLE CONTAMINANTS
Water
• Low-chain hydrocarbons
• Inorganic compounds
• Salts
• Some organic acids and other polar compounds
Dilute Acids
• Basic (caustic) compounds
• Amines
• Hydrazines
Dilute Bases -- for example, detergent
and soap
• Metals
• Acidic compounds
• Phenol
• Thiols
• Some nitro and sulfonic compounds
Organic Solvents ’ - for example,
alcohols, ethers, ketones, aromatics,
straight-chain alkanes (e.g., hexane), and
common petroleum products (e.g., fuel,
oil, kerosene)
• Nonpolar compounds (e.g., some organic compounds)
- WARNING: Some organic solvents can permeate and/or degrade protective clothing.
A rinsate blank consists of a sample of analyte-free
(i e, deionized) water which is passed over and
through a field decontaminated sampling device and
placed in a clean sample container.
Rinsate blanks should be run for all parameters of
interest at a rate of 1 per 20 for each parameter,
even if samples are not shipped that day. Rinsate
blanks are not required if dedicated sampling
equipment is used.
1.10 DATA VALtDATION
This section is not applicable to this SOP.
1.11 HEALTH AND SAFETY
When working with potentially hazardous materials,
follow U.S EPA, OSHA and specific health and
safety procedures.
Decontamination can pose hazards under certain
circumstances even though performed to protect
health and safety. Hazardous substances may be
incompatible with decontamination methods. For
example, the decontamination solution or solvent
may react with contaminants to produce heat,
explosion, or tc dc products. Decontamination
methods may be incompatible with clothing or
equipment; some solvents can permeate or degrade
protective clothing. Also, decontamination solutions
and solvents may pose a direct health hazard to
workers through inhalation or skin contact, or if
they combust.
The decontamination solutions and solvents must be
determined to be compatible before use. Any
method that permeates, degrades, or damages
personal protective equipment should not be used.
If decontamination methods pose a direct health
hazard, measures should be taken to protect
personnel or the methods should be modified to
eliminate the hazard
4
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2.0 DRUM SAMPLING: SOP #2009
2.1 SCOPE AND APPLICATION
The purpose of this Standard Operating Procedure
(SOP) is to provide technical guidance on safe and
cost-effective response actions at hazardous waste
sites containing drums with unknown contents.
Container contents are sampled and characterized
for disposal, bulking, recycling, grouping, and/or
classification purposes.
2.2 METHOD SUMMARY
Prior to sampling, drums must be inventoried,
staged, and opened. An inventory entails recording
visual qualities of each drum and any characteristics
pertinent to the contents’ classification. Staging
involves the organization, and sometimes
consolidation of drums which have similar wastes or
characteristics Opening of closed drums can be
performed manually or remotely. Remote drum
opening is recommended for worker safety. The
most widely used method of sampling a drum
involves the use of a glass thief. This method is
quick, simple, relatively inexpensive, and requires no
decontamination.
2.3 SAMPLE PRESERVATION,
CONTAINERS, HANDLING, AND
STORAGE
Samples collected from drums are considered waste
samples. No preservatives should be added since
there is a potential reaction of the sample with the
preservative. Samples should, however, be cooled
to 4°C and protected from sunlight in order to
minimize any potential reaction due to the light
sensitivity of the sample.
Sample bottles for collection of waste liquids,
sludges, or solids are typically wide-mouth amber
jars with Teflon-lined screw caps. Actual volume
required for analysis should be determined in
conjunction with the laboratory performing the
analysis.
Follow these waste sample handling procedures:
1 Placc sample container in two Ziploc plastic bags.
2. Place each bagged container in a 1-gallon
covered can containing absorbent packing
material Place the lid on the can.
3. Mark the sample identification number on the
outside of the can.
4. Place the marked cans in a cooler, and fill
remaining space with absorbent packing
material.
5. Fill out chain of custody form for each cooler,
place in plastic, and affix to inside lid of cooler.
6. Secure and custody seal the lid of cooler.
7. Arrange for the appropriate transportation
mode consistent with the type of hazardous
waste involved.
2.4 INTERFERENCES AND
POTENTIAL PROBLEMS
The practice of tapping drums to determine their
contents is neither safe nor effective and should not
be used if the drums are visually overpressurized or
if shock-sensitive materials are suspected. A laser
thermometer may be used instead.
Drums that have been overpressurized, to the extent
that the head is swollen several inches above the
level of the chime, should not be moved. A number
of devices have been developed for venting critically
swollen drums. One method that has proven to be
effective is a tube and spear device. A light
aluminum tube (3 meters long) is positioned at the
vapor space of the drum. A rigid, hooking device
attached to the tube goes over the chime and holds
the tube securely in place. The spear is inserted in
the tube and positioned against the drum wall. A
sharp blow on the end of the spear drives the
sharpened tip through the drum and the gas vents
along the grooves. The venting should be done
from behind a wall or barricade. This device can be
cheaply and easily designed and constructed where
needed Once the pressure has been relieved, the
bung can be removed and the drum sampled.
5
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2.5 EQUIPMENT/APPARATUS
The following are standard materials and equipment
required for sampling:
• personal protection equipment
• wide-mouth glass jars with Teflon cap liner,
approximately 500 mL volume
• uniquely numbered sample identification
labels with corresponding data sheets
• 1-gallon covered cans half-filled with
absorbent (vermiculite)
• chain of custody forms
• decontamination materials
• glass thief tubes or Composite Liquid
Waste Samplers (COLIWASA)
• laser thermometer
• drum opening devices
Drum opening devices include the followingS
2.5.1 Bung Wrench
A common method for opening drums manually is
using a universal bung wrench. These wrenches
have fittings made to remove nearly all commonly
encountered bungs They are usually constructed of
cast iron, brass, or a bronze-beryllium, non-sparking
alloy formulated to reduce the likelihood of sparks.
The use of a non-sparking bung wrench does not
completely eliminate the possibility of a spark being
produced. (See Figure 1, Appendix B.)
2.5.2 Drum Deheader
When a bung is not removable with a bung wrench,
a drum can be opened manually by using a drum
deheader. This tool is constructed of forged steel
with an alloy steel blade and is designed to cut the
lid of a drum off or part way off by means of a
scissors-like cutting action. A limitation of this
device is that it can he attached only to closed head
drums. Drums with removable heads must be
opened by other means. (See Figure 2, Appendix
B,)
2.5.3 Hand Pick, Pickaxe, and Hand
Spike
These tools are usually constructed of brass or a
non-sparking alloy with a sharpened point that can
penetrate the drum lid or head when the tool is
swung The hand picks or pickaxes that are most
commonly used are commercially available; whereas
the spikes are generally uniquely fabricated 4-foot
long poles with a pointed end. (See Figure 3,
Appendix B.)
2.5.4 Backhoe Spike
The most common means used to open drums
remotely for sampling is the use of a metal spike
attached or welded to a backhoe bucket. In
addition to being very efficient, this method can
greatly reduce the likelihood of personal exposure.
(See Figure 4, Appendix B.)
2.5.5 Hydraulic Drum Opener
Another remote method for opening drums is with
remotely operated hydraulic devices. One such
device uses hydraulic pressure to pierce through the
wall of a drum. It consists of a manually operated
pump which pressurizes soil through a length of
hydraulic line. (See Figure 5, Appendix B.)
2.5.6 Pneumatic Devices
A pneumatic bung remover consists of a
compressed air supply that is controlled by a heavy-
duty, two.stage regulator. A high-pressure air line
of desired length delivers compressed air to a
pneumatic drill, which is adapted to turn a bung
fitting selected to fit the bung to be removed. An
adjustable bracketing system has been designed to
position and align the pneumatic drill over the bung.
This bracketing system must be attached to the
drum before the drill can be operated. Once the
bung has been loosened, the bracketing system must
be removed before the drum can be sampled. This
remote bung opener does not permit the slow
venting of the container, and therefore appropriate
precautions must be taken. It also requires the
container to be upright and relatively level. Bungs
that are rusted shut cannot be removed with this
device. (See Figure 6, Appendix B.)
2.6 REAGENTS
Reagents are not typically ;?quired for preserving
drum samples. However, reagents are used for
decontaminating sampling equipment.
Decontamination solutions are specified in ERT
SOP #2006, Sampling Equipment Decontamination.
6
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2.7 PROCEDURES
2.7.1 Preparation
1, Determine the extent of the sampling effort, the
sampling methods to be employed, and which
equipment and supplies are needed.
2. Obtain necessary sampling and monitoring
equipment.
3. Decontaminate or preclean equipment, and
ensure that it is in working order.
4. Prepare scheduling and coordinate with staff,
clients, and regulatory agency, if appropriate.
5. Perform a general site survey prior to site entry
in accordance with the site-specific health and
safety plan.
6. Use stakes, flagging, or buoys to identify and
mark all sampling locations. If required, the
proposed locations may be adjusted based on
site access, property boundaries, and surface
obstructions.
2.7.2 Drum Inspection
Appropriate procedures for handling drums depend
on the contents. Thus, prior to any handling, drums
should be visually inspected to gain as much
information as possible about their contents. Those
in charge of inspections should be on the look-out
for:
• drum condition, corrosion, rust, and leaking
contents
• symbols, words, or other markings on the drum
indicating hazards (i.e., explosive, radioactive,
toxic, flammable)
• signs that the drum is under pressure
• shock sensitivity
Monitor around the drums with radiation
Instruments, organic vapor monitors (OVA) and
combustible gas indicators (CGI).
Classify the drums into categories, for instance:
• radioactive
• leaking/deteriorating
• bulging
• drums containing lab packs
• explosive/shock sensitive
All personnel should assume that unmarked drums
contain hazardous materials until their contents
have been categorized, and that labels on drums
may not accurately describe their contents.
If it is presumed that there are buried drums on-
site, geophysical investigation techniques such as
magnetometry, ground penetrating radar, and metal
detection can be employed in an attempt to
determine depth and location of the drums. See
ERT SOP #2159, General Surface Geophysics.
2.7.3 Drum Staging
Prior to sampling, the drums should be staged to
allow easy access. Ideally, the staging area should
be located just far enough from the drum opening
area to prevent a chain reaction if one drum should
explode or catch fire when opened.
While staging, physically separate the drums into
the following categories: those containing liquids,
those containing solids, lab packs, or gas cylinders,
and those which are empty. This is done because
the strategy for sampling and handling
drums/containers in each of these categories will be
different. This may be achieved by
• Visual inspection of the drum and its
labels, codes, etc. Solids and sludges are
typically disposed of in open-top drums.
Closed-head drums with a bung opening
generally contain liquid.
• Visual inspection of the contents of the
drum during sampling followed by
restaging, if needed.
Once a drum has been excavated and any
immediate hazard has been eliminated by
overpacking or transferring the drum’s contents,
affix a numbered tag to the drum and transfer it to
a staging area. Color-coded tags, labels, or bands
should be used to mark similar waste types. Record
a description of each drum, its condition, any
unusual markings, and the location where it was
buried or stored, on a drum data sheet (Appendix
A). This data sheet becomes the principal
7
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recordkeeping tool for tracking the drum onsite.
1. Fully outfit field personnel with protective gear.
Where there is good reason to suspect that some
drums contain radioactive, explosive, and shock-
sensitive materials, these drums should be staged in
a separate, isolated area. Placement of explosives
and shock-sensitive materials in dtked and fenced
areas will minimize the hazard and the adverse
effects of any premature detonation of explosives.
Where space allows, the drum opening area should
be physically separated from the drum removal and
drum staging operations. Drums are moved from
the staging area to the drum opening area one at a
time using forklift trucks equipped with drum
grabbers or a barrel grappler. In a large-scale drum
handling operation, drums may be conveyed to the
drum opening area using a roller conveyor.
2.7.4 Drum Opening
There are three basic techniques available for
opening drums at hazardous waste sites:
• Manual opening with non-sparking bung
wrenches,
• Drum deheading, and
• Remote drum puncturing or bung removal.
The choice of drum opening techniques and
accessories depends on the number of drums to be
opened, their waste contents, and physical condition.
Remote drum opening equipment should always be
considered in order to protect worker safety.
Under OSHA 1910.120, manual drum opening with
bung wrenches or deheaders should be performed
only with structurally sound drums having contents
that are known to be (1) not shock sensitive, (2)
non-reactive, (3) non-explosive, and (4) non-
flammable.
Manual Drum Opening with a Bung
Wrench
Manual drum opening with bung wrenches (Figure
1, Appendix B) should not be performed unless the
drums are structurally sound (no evidence of
bulging or deformation) and their contents are
known to be non-explosive. If opening the drum
with bung wrenches is deemed reasonably cost-
effective and safe, then follow these procedures to
minimize the hazard.
2. Position drum upright with the bung up, or, for
drums with bungs on the side, lay the drum on
its side with the bung plug up.
3 Wrench the bung with a slow, steady pulling
motion across the drum. If the length of the
bung wrench handle provides inadequate
leverage for unscrewing the plug, attach a
“cheater bar” to the handle to improve leverage.
Manual Drum Opening with a Drum
Deheader
Drums are opened with a drum deheader (Figure 2,
Appendix B) by first positioning the cutting edge
just inside the top chime and then tightening the
adjustment screw so that the deheader is held
against the side of the drum. Moving the handle of
the deheader up and down while sliding the
deheader along the chime will cut off the entire top.
lithe top chime of a drum has been damaged or
badly dented, it may not be possible to cut off the
entire top. Since there is always the possibility that
a drum may be under pressure, make the initial cut
very slowly to allow for the gradual release of any
built-up pressure. A safer technique would be to
use a remote method to puncture the drum prior to
using the deheader.
Self-propelled drum openers which are either
electrically or pneumatically driven can be used for
quicker and more efficient deheading.
Manual Drum Opening with a Hand
Pick, Pickaxe, or Spike
When a drum must be opened and neither a bung
wrench nor a drum deheader is suitable, the drum
can be opened for sampling by using a hand pick,
pickaxe, or spike (Figure 3, Appendix B). Often the
drum lid or head must be hit with a great deal of
force in order to penetrate it. The potential for
splash or spraying is greater than with other
opening methods and, therefore, this method of
drum opening is not recommended, particularly
when opening drums containing liquids. Some
spikes used have been modified by the addition of
a circular splash plate near the penetrating end.
This plate acts as a shield and reduces the amount
of splash in the direction of the person using the
spike. Even with this shield, good splash gear is
essential
8
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2.7.5 Drum Sampling
Since drums cannot be opened slowly with these
tools, spray from drums is common requiring
appropriate safety measures. Decontaminate the
pick or spike after each drum is opened to avoid
cross-contamination and/or adverse chemical
reaction from incompatible materials.
Remote Drum Opening with a Backhoe
Spike
Remotely operated drum opening tools are the
safest available means of drum opening. Remote
drum opening is slow, but is much safer compared
to manual methods of opening.
Drums should be ‘staged’ or placed in rows with
adequate aisle space to allow ease in backhoe
maneuvering Once staged, the drums can be
quickly opened by punching a hole in the drum
head or lid with the spike.
The spike (Figure 4, Appendix B) should be
decontaminated after each drum is opened to
prevent cross-contamination. Even though some
splash or spray may occur when this method is used,
the operator of the backhoe can be protected by
mounting a large shatter-resistant shield in front of
the operator’s cage. This, combined with the
required level of personal protection gear, should be
sufficient to protect the operator. Additional
respiratory protection can be afforded by providing
the operator with an on-board airline system.
Remote Drum Opening with Hydraulic
Devices
A piercing device with a metal point is attached to
the end of a hydraulic line and is pushed into the
drum by hydraulic pressure (Figure 5, Appendix B).
The piercing device can be attached so that the
sampling hole can be made on either the side or the
head of the drum. Some of the metal piercers are
hollow or tube-like so that they can be left in place
if desired and serve as a permanent tap or sampling
port The picrccr is designed to establish a tight
seal after penetrating the container.
Remote Drum Opening with Pneumatic
Devices
Pneumatically-operated devices ut ili7lng corn pressed
air have been designed to remove drum bungs
remotely (Figure 6, Appendix B)
After the drum has been opened, monitor
headspace gases using an explosimeter and organic
vapor analyzer. In most cases it is impossible to
observe the contents of these sealed or partially
sealed vessels. Since some layering or stratification
is likely in any solution left undisturbed over time,
take a sample that represents the entire depth of
the vessel.
When sampling a previously sealed vessel, check for
the presence of a bottom sludge. This is easily
accomplished by measuring the depth to the
apparent bottom, then comparing it to the known
interior depth.
Glass Thief Sampler
The most widely used implement for sampling is a
glass tube commonly referred to as a glass thief
(Figure 7, Appendix B). This tool is simple, cost
effective, quick, and collects a sample without
having to decontaminate. Glass thieves are typically
6mm to 16mm l.D. and 48 inches long.
Procedures for using a glass thief are as follows:
1. Remove cover from sample container.
2. Insert glass tubing almost to the bottom of the
drum or until a solid layer is encountered.
About one foot of tubing should extend above
the drum.
3. Allow the waste in the drum to reach its
natural level in the tube.
4. Cap the top of the sampling tube with a
tapered stopper or thumb, ensuring liquid docs
not come into contact with stopper.
5. Carefully remove the capped tube from the
drum and insert the uncapped end in the
sample container.
6. Release stopper and allow the glass thief to
drain until the container is approximately 2/3
full.
7. Remove tube from the sample container, break
it into pieces and place the pieces in the drum.
9
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8. Cap the sample container tightly and place
prelabeled sample container in a carrier.
9. Replace the bung or place plastic over the
drum.
10. Log all samples in the site logbook and on field
data sheets.
11. Package samples and complete necessary
paperwork.
12. Transport sample to decontamination zone to
prepare it for transport to the analytical
laboratory.
In many instances a drum containing waste material
will have a sludge layer on the bottom. Slow
insertion of the sample tube down into this layer
and then a gradual withdrawal will allow the sludge
to act as a bottom plug to maintain the fluid in the
tube. The plug can be gently removed and placed
into the sample container by the use of a stainless
steel lab spoon.
It should be noted that in some instances disposal
of the tube by breaking it into the drum may
interfere with eventual plans for the removal of its
contents. This practice should be cleared with the
project officer or other disposal techniques
evaluated.
COLIWASA Sampler
Some equipment is designed to collect a sample
from the full depth of a drum and maintain it in the
transfer tube until delivery to the sample bottle.
These designs include primarily the Composite
Liquid Waste Sampler (COLIWASA) and
modifications thereof. The COLIWASA (Figure 8,
Appendix B) is a much cited sampler designed to
permit representative sampling of multiphase wastes
from drums and other containerized wastes. One
configuration consists of a 152 cm by 4 cm I.D.
section of tubing with a neoprene stopper at one
end attached by a rod running the length of the
tube to a locking mechanism at the other end.
Manipulation of the locking mechanism opens and
closes the sampler by raising and lowering the
neoprene stopper. One model of the COLIWASA
is shown in Appendix B; however, the design can be
modified and/or adapted somewhat to meet the
needs of the sampler.
The major drawbacks associated with using a
COLIWASA concern decontamination and costs.
The sampler is difficult, if not impossible to
decontaminate in the field and its high cost in
relation to alternative procedures (glass tubes) make
it an impractical throwaway item. It still has
applications, however, especially in instances where
a true representation of a multiphase waste is
absolutely necessary.
Follow these procedures for using the COLIWASA:
1. Put the sampler in the open position by placing
the stopper rod handle in the 1-position and
pushing the rod down until the handle sits
against the sampler’s locking block.
2. Slowly lower the sampler into the liquid waste.
Lower the sampler at a rate that permits the
levels of the liquid inside and outside the
sampler tube to be about the same. If the level
of the liquid in the sample tube is lower than
that outside the sampler, the sampling rate is
too fast and will result in a non-representative
sample.
3. When the sampler stopper hits the bottom of
the waste container, push the sampler tube
downward against the stopper to dose the
sampler. Lock the sampler in the dosed
position by turning the T-handle until it is
upright and one end rests tightly on the locking
block.
4. Slowly withdraw the sample from the waste
container with one hand while wiping the
sampler tube with a disposable cloth or rag
with the other hand.
5. Carefully discharge the sample into a suitable
sample container by slowly pulling the lower
end of the T-handle away from the locking
block while the lower end of the sampler is
positioned in a sample container.
6. Cap the sample container tightly and place
prelabeled sample container in a carrier.
7. Replace the bung or place plastic over the
drum.
8. Log all samples in the site logbook and on field
data sheets.
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9. Package samples and complete necessary 2.10 DATA VALIDATION
paperwork.
This section is not applicable to this SOP.
10 Transport sample to decontamination zone to
prepare it for transport to the analytical
laboratory. 2.11 HEALTH AND SAFETY
When working with potentially hazardous materials,
2.8 CALCULATIONS follow U.S. EPA, OSHA, and specific health and
safety procedures.
This section is not applicable to this SOP.
The opening of closed containers is one of the most
hazardous site activities. Maximum efforts should
2.9 QUALITY ASSURANCE/ be made to ensure the safety of the sampling team.
QUALITY CONTROL Proper protective equipment and a general
awareness of the possible dangers will minimize the
The following general quality assurance procedures risk inherent in sampling operations. Employing
apply: proper drum-opening techniques and equipment will
also safeguard personnel Use remote sampling
• Document all data on standard chain of equipment whenever feasible.
custody forms, field data sheets, or within
site logbooks.
• Operate all instrumentation in accordance
with operating instructions as supplied by
the manufacturer, unless otherwise
specified in the work plan. Equipment
checkout and calibration activities must
occur prior to sampling/operation, and
they must be documented.
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3.0 TANK SAMPLING: SOP #2010
3.1 SCOPE AND APPLICATION
The purpose of this Standard Operating Procedure
(SOP) is to provide protocols for sampling tanks
and other confined spaces from outside the vessel.
3.2 METHOD SUMMARY
The safe collection of a representative sample
should be the criterion for selecting sample
locations. A representative sample can be collected
using techniques or equipment that are designed for
obtaining liquids or sludges from various depths.
The structure and characteristics of storage tanks
present problems with collection of samples from
more than one location; therefore, the selection of
sampling devices is an important consideration.
Depending on the type of vessel and characteristics
of the material to be sampled, one can choose a
bailer, glass thief, bacon bomb sampler, sludge
judge, COLIWASA, or subsurface grab sampler to
collect the sample. For depths of less than 5-feet,
a bailer, COLIWASA, or sludge judge can be used.
A sludge judge, subsurface grab sampler, bailer, or
bacon bomb sampler can be used for depths greater
than S-feet. A sludge judge or bacon bomb can be
used to determine if the tank consists of various
strata.
All sample locations should be surveyed for air
quality prior to sampling. At no time should
sampling continue with an LEL reading greater than
25%.
All personnel involved in tank sampling should be
advised as to the hazards associated with working in
unfavorable conditions.
3.3 SAMPLE PRESERVATION,
CONTAINERS, HANDLING, AND
STORAGE
Samples collected from tanks are considered waste
samples and, as such, addition of preservatives is
not required due to the potential reaction of the
sample with the preservative. Samples should,
however, be cooled to 4°C and protected from
sunlight in order to minimize any potential reaction
due to the light sensitivity of the sample.
Sample bottles for collection of waste liquids,
sludges, or solids are typically wide-mouth amber
jars with Teflon-lined screw caps. Actual volume
required for analysis should be determined in
conjunction with the laboratory performing the
analysis.
Waste sample handling procedures should be as
follows:
1. Place sample container in two Ziploc plastic
bags.
2. Place each bagged container in a 1-gallon
covered can containing absorbent packing
material. Place the lid on the can.
3. Mark the sample identification number on the
outside of the can.
4. Place the marked cans in a cooler, and fill
remaining space with absorbent packing
material.
5. Fill out a chain of custody form for each
cooler, place it in plastic, and affix it to the
inside lid of the cooler.
6. Secure and custody seal the lid of cooler.
7. Arrange for the transportation appropriate for
the type of hazardous waste involved.
3.4 INTERFERENCES AND
POTENTIAL PROBLEMS
Sampling a storage tank requires a great deal of
manual dexterity, often requiring the sampler to
climb to the top of the tank upon a narrow vertical
or spiral stairway or ladder while wearing protective
clothing and carrying sampling equipment.
Before climbing onto the vessel, perform a
structural survey of the tank to ensure the sampler’s
13
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s . c .y and accessibility prior to initiating field
activities.
As in all opening of containers, take extreme
caution to avoid ignition or combustion of volatile
contents. All tools used must be constructed of a
non-sparking material and electronic instruments
must be intrinsically safe.
All sample locations should be surveyed for air
quality prior to sampling. At no time should
sampling continue with an LEL reading greater than
25%.
3.5 EQUIPMENT/APPARATUS
Storage tank materials include liquids, sludges, still
bottoms, and solids of various structures. The type
of sampling equipment chosen should be compatible
with the waste. Samplers commonly used for tanks
include: the bacon bomb sampler, the sludge judge,
glass thief, bailer, COLt WASA, and subsurface grab
sampler.
sampling plan
safety equipment
tape measure
weighted tape line or equivalent
camera/film
stainless steel bucket or bowl
sample containers
Ziploc plastic bags
logbook
labels
field data sheets
chain of custody forms
flashlight (explosion proof)
coolers
ice
decontamination supplies
bacon bomb sampler
sludge judge
glass thief
bailer
COLIWASA
subsurface grab sampler
water/oil level indicator
OVA (organic vapor analyzer or
equivalent)
• explosimeter/oxygen meter
• high volume blower
3.6 REAGENTS
Reagents are not typically required for the
preservation of waste samples. However, reagents
will be utilized for decontamination of equipment.
Decontamination solutions required are specified in
ERT SOP #2006, Sampling Equipment
Decontamination.
3.7 PROCEDURES
3.7.1 PreparatIon
1. Determine the extent of the sampling effort,
the sampling methods to be employed, and
which equipment and supplies are needed.
2. Obtain necessary sampling and monitoring
equipment.
3. Decontaminate or preclean equipment, and
ensure that it is in working order.
4. Prepare scheduling and coordinate with staff,
clients, and regulatory agency, if appropriate.
5. Perform a general site survey prior to site entry
in accordance with the site-specific health and
safety plan.
6. Identify and mark all sampling locations.
3.7.2 Preliminary Inspection
1. Inspect the external structural characteristics of
each tank and record in the site logbook
Potential sampling points should be evaluated
for safety, accessibility, and sample quality.
2. Prior to opening a tank for internal inspection,
the tank sampling team should:
• Review safety procedures and emergency
contingency plans with the Safety Officer,
• Ensure that the tank is properly grounded,
• Remove all sources of ignition from the
immediate area.
3. Each tank should be mounted using
appropriate means. Remove manway covers
using non-sparking tools.
•
•
•
•
•
•
•
•
•
•
•
•
14
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4. Collect air quality measurements for each
potential sample location using an
explosimeter/oxygen meter for a lower
explosive limit (LEL/0 2 ) reading and an
OVA/HNU for an organic vapor concentration.
Both readings should be taken from the tank
headspace, above the sampling port, and in the
breathing zone.
5. Prior to sampling, the tank headspace should be
cleared of any toxic or explosive vapor
concentration using a high volume blower. No
work should start if LEL readings exceed 25%.
At 10% LEL, work can continue but with
extreme caution.
3.7.3 Sampling Procedures
Determine the depth of any and all liquid-solid
interface, and depth of sludge using a weighted
tape measure, probe line, sludge judge, or
equivalent.
2. Collect liquid samples from 1-foot below the
surface, from mid-depth of liquid, and from 1-
foot above the bottom sludge layer. This can
be accomplished with a subsurface grab sampler
or bacon bomb. For liquids less than 5-feet in
depth, use a glass thief or COLIWASA to
collect the sample.
If sampling storage tanks, vacuum trucks, or
process vessels, collect at least one sample from
each compartment in the tank. Samples should
always be collected through an opened hatch at
the top of the tank. Valves near the bottom
should not be used, because of their
questionable or unknown integrity. If such a
valve cannot be closed once opened, the entire
tank contents may be lost to the ground
surface. Also, individual strata cannot be
sampled separately through a valve near the
bottom.
3. Compare the three samples for visual phase
differences. If phase differences appear,
systematic iterative sampling should be
performed. By halving the distance between
two discrete sampling points, one can determine
the depth of the phase change.
4. If another sampling port is available, sample as
above to verify the phase information
5. Measure the outside diameter of the tank and
determine the volume of wastes using the depth
measurements. (See Appendix C for
calculations.)
6. Sludges can be collected using a bacon bomb
sampler, glass thief, or sludge judge.
7. Record all information on the sample data
sheet or site logbook. Label the container with
the appropriate sample tag.
8. Decontaminate sampling equipment as per
ERT Sop #2006, Sampling Equipment
Decontamination.
3.7.4 Sampling Devices
Bacon Bomb Sampler
The bacon bomb sampler (Figure 9, Appendix B) is
designed to collect material from various levels
within a storage tank. It consists of a cylindrical
body, usually made of chrome-plated brass and
bronze with an internal tapered plunger that acts as
a valve to admit the sample. A line attached to the
top of the plunger opens and closes the valve. A
linc is attached to the removable top cover which
has a locking mechanism to keep the plunger closed
after sampling.
1 Attach the sample line and the plunger line to
the sampler.
2. Measure and then mark the sampling line at
the desired depth.
3. Gradually lower the bacon bomb sampler by
the sample line until the desired level is
reached.
4. When the desired level is reached, pull up on
the plunger line and allow the sampler to fill
before releasing the plunger line to seal off the
sampler.
S. Retrieve the sampler by the sample line. Be
careful not to pull up on the plunger line and
thereby prevent accidental opening of the
bottom valve.
6. Rinse or wipe off the exterior of the sampler
body.
15
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7. Position the sampler over the sample container 8. Package samples and complete necessary
and release its contents by pulling up on the paperwork.
plunger line.
9. Transport sample to decontamination zone to
8. Cap the sample container tightly and place prepare it for transport to the analytical
prelabeled sample container in a carrier, laboratory.
9. Replace the bung or place plastic over the tank. Subsurface Grab Sampler
10. Log all samples in the site logbook and on field Subsurface grab samplers (Figure 11, Appendix B)
data sheets and label all samples. are designed to collect samples of liquids at various
depths. The sampler is usually constructed of
11. Package samples and complete necessary aluminum or stainless steel tubing with a
paperwork. polypropylene or Teflon head that attaches to a 1-
liter sample container.
12. Transport sample to decontamination zone to
prepare it for transport to the analytical 1. Screw the sample bottle onto the sampling
laboratory. head.
Sludge Judge 2. Lower the sampler to the desired depth.
A sludge judge (Figure 10, Appendix B) is used for 3. Pull the ring at the top which opens the spring-
obtaining an accurate reading of solids which can loaded plunger in the head assembly
settle, in any liquid, to any depth. The sampler
consists of 3/4-inch plastic pipe in 5-foot sections, 4. When the bottle is full, release the ring, lift
marked at 1-foot increments, with screw-style sampler, and remove sample bottle.
fittings. The top section includes a nylon line for
raising the sampler. 5. Cap the sample container tightly and place
prelabeled sample container in a carrier.
1. Lower the sludge judge to the bottom of the
tank. 6. Replace the bung or place plastic over the tank.
2. When the bottom has been reached, and the 7. Log all samples in the site logbook and on field
pipe has filled to surface level, tug slightly on data sheets and label all samples.
the rope as you begin to raise the unit. This
will seat the check valve, trapping the column of 8. Package samples and complete necessary
material, paperwork.
3. When the unit has been raised clear of the tank 9. Transport sample to decontamination zone to
liquid, the amount of sludge in the sample can prepare it for transport to the analytical
be read using the 1-foot increments marked on laboratory.
the pipe sections.
Glass Thief
4. By touching the pin extending from the bottom
section against a hard surface, the material is The most widely used implement for sampling is a
released from the unit, glass tube commonly referred to as a glass thief
(Figure 7, Appendix B). This tool is simple, cost
S. Cap the sample container tightly and place effective, quick, and collects a sample without
prelabeled sample container in a carrier, having to decontaminate. Glass thieves are typically
6mm to 16mm 1.D. and 48 inches long.
6. Replace the bung or place plastic over the tank.
1. Remove cover from sample container.
7. Log all samples in the site logbook and on field
data sheets and label all samples 2. Insert glass tubing almost to the bottom of the
16
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tank or until a solid layer is encountered.
About 1 Foot of tubing should extend above the
tank.
3. Allow the waste in the tank to reach its natural
level in the tube.
4. Cap the top of the sampling tube with a
tapered stopper or thumb, ensuring liquid does
not come into contact with stopper.
5. Carefully remove the capped tube from the
tank and insert the uncapped end in the sample
container. Do not spill liquid on the outside of
the sample container.
6. Release stopper and allow the glass thief to
drain until the container is approximately 2/3
full.
7. Remove tube from the sample container, break
it into pieces and place the pieces in the tank.
8. Cap the sample container tightly and place
prelabeled sample container in a carrier.
9. Replace the bung or place plastic over the tank.
10. Log all samples in the site logbook and on field
data sheets and label all samples.
11. Package samples and complete necessary
paperwork.
12. Transport sample to decontamination zone to
prepare it for transport to the analytical
laboratory.
In many instances a tank containing waste material
will have a sludge layer on the bottom. Slow
insertion of the sample tube down into this layer
and then a gradual withdrawal will allow the sludge
to act as a bottom plug to maintain the fluid in the
tube. The plug can be gently removed and placed
into the sample container by the use of a stainless
steel lab spoon.
Bailer
The positive-displacement volatile sampling bailer
(manufactured by GPI or equivalent) (Figure 12,
Appendix B) is perhaps the most appropriate for
collecting water samples for volatile analysis. Other
bailer types (messenger, bottom fill, etc.) are less
desirable, but may be mandated by cost and site
conditions. Generally, ballets can provide an
acceptable sample, providing that the sampling
personnel use extra care in the collection process.
1. Make sure clean plastic sheeting surrounds the
tank.
2. Attach a line to the bailer.
3. Lower the bailer slowly and gently into the tank
so as not to splash the bailer into the tank
contents.
4. Allow the bailer to fill completely and retrieve
the bailer from the tank.
5. Begin slowly pouring from the bailer.
6. Cap the sample container tightly and place
prelabeled sample container in a carrier.
7. Replace the bung or place plastic over the tank.
8. Log all samples in the site logbook and on field
data sheets and label all samples.
9. Package samples and complete necessary
paperwork.
10. Transport sample to decontamination zone to
prepare it for transport to an analytical
laboratory.
COLIWASA
Some equipment is designed to collect a sample
from the full depth of a tank and maintain it in the
transfer tube until delivery to the sample boLtie.
These designs include primarily the composite
Liquid Waste Sampler (COLIWASA) (Figure 8,
Appendix B) and modifications thereof. The
COLIWASA is a much cited sampler designed to
permit representative sampling of multiphase wastes
from tanks and other containerized wastes. One
configuration consists of a 152 cm by 4 cm l.D.
section of tubing with a neoprene stopper at one
end attached by a rod running the length of the
tube to a locking mechanism at the other end.
Manipulation of the locking mechanism opens and
closes the sampler by raising and lowering the
neoprene stopper.
17
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The major drawbacks associated with using a
COLIWASA concern decontamination and costs
The sampler is difficult if not impossible to
decontaminate in the field and its high cost in
relation to alternative procedures (glass tubes) make
it an impractical throwaway item. It still has
applications, however, especially in instances where
a true representation of a multiphase waste is
absolutely necessary.
1 Put the sampler in the open position by placing
the stopper rod handle in the T-position and
pushing the rod down until the handle sits
against the sampler’s locking block.
2 Slowly lower the sampler into the liquid waste.
Lower the sampler at a rate that permits the
levels of the liquid inside and outside the
sampler tube to be about the same. If the level
of the liquid in the sample tube is lower than
that outside the sampler, the sampling rate is
too fast and will result in a non-representative
sample.
3. When the sampler stopper hits the bottom of
the waste container, push the sampler tube
downward against the stopper to close the
sampler. Lock the sampler in the closed
position by turning the T-handle until it is
upright and one end rests tightly on the locking
block.
4. Slowly withdraw the sample from the waste
container with one hand while wiping the
sampler tube with a disposable cloth or rag with
the other hand.
5 Carefully discharge the sample into a suitable
sample container by slowly pulling the lower
end of the T-handle away from the locking
block while the lower end of the sampler is
positioned in a sample container.
6. Cap the sample container tightly and place
prelabeled sample container in a carrier.
7 Replace the bung or place plastic over the tank.
8 Log all samples in the site logbook and on field
data sheets and label all samples
9 Package samples and complete necessary
paperwork
10 Transport sample to decontamination zone to
prepare it for transport to the analytical
laboratory.
3.8 CALCULATIONS
Refer to Appendix C for calculations to determine
tank volumes.
3.9 QUALITY ASSURANCE/
QUALITY CONTROL
There are no specific quality assurance activities
which apply to the implementation of these
procedures. However, the following general QA
procedures apply:
• All data must be documented on field data
sheets or within site logbooks.
• All instrumentation must be operated in
accordance with operating instructions s
supplied by the manufacturer, unless
otherwise specified in the work plan.
Equipment checkout and calibration
activities must occur prior to
sampling/operation and they must be
documented
3.10 DATA VALIDATION
This section is not applicable to this SOP.
3.11 HEALTH AND SAFETY
When working with potentially hazardous materials,
follow U.S. EPA, OSHA, and specific health and
safety procedures. More specifically, the hazards
associated with tank sampling may cause bodily
injury, illness, or death to the worker. Failure to
recognize potential hazards of waste containers is
the cause of most accidents. It should be assumed
that the most unfavorable conditions exist, and that
the danger of explosion and poisoning will be
present. Hazards specific to tank sampling are:
• Hazardous atmospheres can be flammable,
toxic, asphyxiating, or corrosive.
• If activating electrical or mechanical
equipment would cause injury, each piece
of equipment should be manually isolated
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to prevent inadvertent activation while
workers are occupied.
• Communication is of utmost importance
between the sampling worker and the
standby person to prevent distress or injury
going unnoticed. The Illuminating
Engineers Society Lighting Handbook
requires suitable illumination to provide
sufficient visibility for work.
• Noise reverberation may disrupt verbal
communication with standby personnel.
• Tank vibration may affect multiple body
parts and organs of the sampler depending
on vibration characteristics.
• General hazards include falling scaffolding,
surface residues (which could cause
electrical shock, incompatible material
reactions, slips, or falls), arid structural
objects (including baffles/trays in
horizontal/vertical tanks, and overhead
structures).
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4.0 CHIP, WIPE, AND SWEEP SAMPLING: SOP #2011
4.1 SCOPE AND APPLICATION
This Standard Operating Procedure (SOP) outlines
the recommended protocol and equipment for
collection of representative chip, wipe, and sweep
samples to monitor potential surficial
Contamination.
This method of sampling is appropriate for surfaces
contaminated with non-volatile species of analytes
(i.e., PCB, PCDD, PCDF, metals, cyanide, etc.)
Detection limits are analyte specific. Sample size
should be determined based upon the detection
limit desired and the amount of sample requested
by the analytical laboratory. Typical sample area is
1 square foot. However, based upon sampling
location, the area may need modification due to
area configuration.
4.2 METHOD SUMMARY
Since surface situations vary widely, no universal
sampling method can be recommended. Rather,
the method and implements used must be tailored
to suit a specific sampling site. The sampling
location should be selected based upon the potential
for contamination as a result of manufacturing
processes or personnel practices.
Chip sampling is appropriate for porous surfaces
and is generally accomplished with either a hammer
and chisel, or an electric hammer. The sampling
device should be laboratory cleaned and wrapped in
clean, autoclaved aluminum foil until ready for use.
To collect the sample, a measured and marked off
area is chipped both horizontally and vertically to an
even depth of 1/8 inch, The sample is then
transferred to the proper sample container.
Wipe samples are collected from smooth surfaces to
indicate suruicial contamination; a sample location
is measured and marked off. Sampling personnel
wear a new pair of surgical gloves to open a sterile
gauze pad, and then soak it with solvent. The
solvent used is dependent on the surface being
sampled. This pad is then stroked firmly over the
sample surface, first vertically, then horizontally, to
ensure complete coverage. The pad is then
transferred to the sample container.
Sweep sampling is an effective method for the
collection of dust or residue on porous or non-
porous surfaces. To collect such a sample, an
appropriate area is measured off. Then, while
wearing a new pair of disposable surgical gloves,
sampling personnel use a dedicated brush to sweep
material into a dedicated dust pan. The sample is
then transferred to the proper sample container.
Samples collected by all three methods are sent to
the laboratory for analysis.
4.3 SAMPLE PRESERVATION,
CONTAINERS, HANDLING, AND
STORAGE
Samples should be stored out of direct sunlight to
reduce photodegredation and shipped on ice (4°C)
to the laboratory performing the analysis.
Appropriately-sized, laboratory-cleaned, glass
sample jars should be used for sample collection.
The amount of sample required is determined in
concert with the analytical laboratory.
4.4 INTERFERENCES AND
POTENTIAL PROBLEMS
This method has few significant interferences or
problems. Typical problems result from rough
porous surfaces which may be difficult to wipe, chip,
or sweep.
4.5 EQUIPMENT/APPARATUs
• lab-clean sample containers of proper size
and composition
• field and travel blanks
• site logbook
• sample analysis request forms
• chain of custody forms
• custody seals
• sample labels
• disposable surgical gloves
• sterile wrapped gauze pad (3 in. x 3 in.)
• appropriate pesticide (HPLC) grade solvent
21
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• medium-sized, laboratory-cleaned paint
brush
• medium-sized, laboratory-cleaned chisel
• autoclaved aluminum foil
• camera
• hexane (pesticide/HPLC grade)
• iso-octane
• distilled/deionized water
4.6 REAGENTS
Reagents are not required for preservation of chip,
wipe or sweep samples. However, reagents will be
utilized for decontamination of sampling equipment.
Decontamination solutions are specified in ERT
SOP #2006, Sampling Equipment Decontamination.
&7 PROCEDuRES
4.7.1 Preparation
1. Determine the extent of the sampling effort, the
sampling methods to be employed, and the
types and amounts of equipment and supplies
needed.
2. Obtain necessary sampling and monitoring
equipment.
3. Decontaminate or preclean equipment, and
ensure that it is in working order.
4. Prepare scheduling and coordinate with staff,
clients, and regulatory agencies, if appropriate.
5. Perform a general site survey prior to site entry
in accordance with the site-specific health and
safety plan.
6. Mark all sampling locations. If required, the
proposed locations may be adjusted based on
site access, property boundaries, and surface
obstructions.
4.7.2 ChIp Sample Collection
Sampling of porous surfaces is generally
accomplished by using a chisel and hammer or
electric hammer. The sampling device should be
laboratory cleaned or field decontaminated as per
ERT SOP# 2006, Sampling Equipment Decon-
tamination. It is then wrapped in cleaned,
autoclaved aluminum foil. The sampler should
remain in this wrapping until it is needed. Each
sampling device should be used for only one sample.
1. Choose appropriate sampling points; measure
off the designated area and photo document.
2. To facilitate later calculations, record surface
area to be chipped.
3. Don a new pair of disposable surgical gloves.
4. Open a laboratory-cleaned chisel or equivalent
sampling device.
5. Chip the sample area horizontally, then
vertically to an even depth of approximately 1/8
inch.
6. Place the sample in an appropriately-prepared
sample container with a Teflon-lined cap.
7. Cap the sample container, attach the label and
custody seal, and place in a double plastic bag.
Record all pertinent data in the site logbook.
Complete the sampling analysis request form
and chain of custody form before taking the
next sample.
8. Store samples out of direct sunlight and cool to
4°C.
9. Leave contaminated sampling device in the
sampled material, unless decontamination is
practical.
10. Follow proper decontamination procedures,
then deliver sample(s) to the laboratory for
analysis.
4.7.3 Wipe Sample Collection
Wipe sampling is accomplished by using a sterile
gauze pad, adding a solvent in which the
contaminant is most soluble, then wiping a pre-
determined, pre-measured area. The sample is
packaged in an amber jar to prevent
photodegradation and packed in coolers for
shipment to the lab. Each gauze pad is used for
only one wipe sample.
1. Choose appropriate sampling points; measure
off the designated area and photo document.
22
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2. To facilitate later calculations, record surface
area to be wiped.
3. Don a new pair of disposable surgical gloves.
4. Open new sterile package of gauze pad.
5. Soak the pad with the appropriate solvent.
6. Wipe the marked surface area using firm
strokes. Wipe vertically, then horizontally to
ensure complete surface coverage.
7. Place the gauze pad in an appropriately
prepared sample container with a Teflon-lined
cap.
8. Cap the sample container, attach the label and
custody seal, and place in a double plastic bag.
Record all pertinent data in the site logbook.
Complete the sampling analysis request form
and chain of custody form before taking the
next sample.
9. Store samples out of direct sunlight and cool to
4°C.
10. Follow proper decontamination procedures,
then deliver sample(s) to the laboratory for
analysis.
4.7.4 Sweep Sample Collection
Sweep sampling is appropriate for bulk
contamination. This procedure utilizes a dedicated,
hand-held sweeper brush to acquire a sample from
a pre-measured area.
1. Choose appropriate sampling points; measure
off the designated area and photo document.
2. To facilitate later calculations, record the
surface area to be swept.
3. Don a new pair of disposable surgical gloves.
4. Sweep the measured area using a dedicated
brush; collect the sample in a dedicated dust
pan.
5. Transfer sample from dust pan to sample
container.
6. Cap the sample container, attach the label and
custody seal, and place in a double plastic bag.
Record all pertinent data in the site logbook.
Complete the sampling analysis request form
and chain of custody form before taking the
next sample.
7. Store samples out of direct sunlight and cool to
4°C.
8. Leave contaminated sampling device in the
sample material, unless decontamination is
practical.
9. Follow proper decontamination procedures,
then deliver sample(s) to the laboratory for
analysis.
4.8 CALCULATIONS
Results are usually provided in mg/g. iig/g or
another appropriate weight per unit weight
measurement. Results may also be given in a mass
per unit area.
4.9 QUALITY ASSURANCE/
QUALITY CONTROL
The following general quality assurance procedures
apply
• All data must be documented on standard
chain of custody forms, field data sheets or
within the site logbook.
• All instrumentation must be operated in
accordance with operating instructions as
supplied by the manufacturer, unless
otherwise specified in the work plan.
Equipment checkout and calibration
activities must occur prior to
sampling/operation, and they must be
documented.
The following specific quality assurance activities
apply to wipe samples:
• A blank should be collected for each
sampling event. This consists of a sterile
gauze pad, wet with the appropriate
solvent, and placed in a prepared sample
container. The blank will help identify
potential introduction of contaminants via
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the sampling methods, the pad, solvent or 4.10 DATA VALIDATION
sample container.
Review the quality control samples and use the data
Spiked wipe samples can also be collected to qualify the environmental results.
to better assess the data being generated.
These are prepared by spiking a piece of
foil of known area with a standard of the 4.11 HEALTH AND SAFETY
analyte of choice. The solvent containing
the standard is allowed to evaporate, and When working with potentially hazardous materials,
the foil is wiped in a manner identical to follow U.S. EPA, OSHA and specific health and
the other wipe samples. safety procedures.
Specific quality assurance activities for chip and
sweep samples should be determined on a site-
specific basis.
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5.0 WASTE PILE SAMPLING: SOP #2017
5.1 SCOPE AND APPLICATION
The objective of this Standard Operating Procedure
(SOP) is to outline the equipment and methods
used in collecting representative samples from waste
piles, sludges or other solid or liquid waste mixed
with soil.
5.2 METHOD SUMMARY
Stainless steel shovels or scoops should be used to
clear away surface material before samples are
collected. For samples at depth, a decontaminated
auger may be required to advance the hole, then
another decontaminated auger used for sample
collection. For a sample core, thin-wall tube
samplers or grain samplers may be used. Near
surfaces samples can be collected with a clean
stainless steel spoon or trowel.
All samples collected, except those for volatile
organic analysis, should be placed into a Teflon.
lined or stainless steel pail and mixed thoroughly
before being transferred to an appropriate sample
container.
5.3 SAMPLE PRESERVATION,
CONTAINERS, HANDLING, AND
STORAGE
Chemical preservation of solids is generally not
recommended. Refrigeration to 4°C is usually the
best approach, supplemented by a minimal holding
time.
Wide mouth glass containers with Teflon.lined caps
are typically used for waste pile samples. Sample
volume required is a function of the analytical
requirements and should be specified in the work
plan.
5.4 INTERFERENCES AND
POTENTIAL PROBLEMS
There are several variables involved in waste
sampling, including shape and size of piles,
compactness, and structure of the waste material.
Shape and size of waste material or waste piles vary
greatly in areal extent and height. Since state and
federal regulations often require a specified number
of samples per volume of waste, size and shape
must be used to calculate volume and to plan for
the correct number of samples. Shape must also be
accounted for when planning physical access to the
sampling point and when selecting the appropriate
equipment to successfully collect the sample at that
location.
Material to be sampled may be homogeneous or
heterogeneous. Homogeneous material resulting
from known situations may not require an extensive
sampling protocol. Heterogeneous and unknown
wastes require more extensive sampling and analysis
to ensure the different components are being
represented.
The term “representative sample” is commonly used
to denote a sample that has the properties and
composition of the population from which it was
collected, in the same proportions as found in the
population. This can be misleading unless one is
dealing with a homogenous waste from which one
sample can represent the whole population.
The usual options for obtaining the most
“representative sample” from waste piles are simple
or stratified random sampling. Simple random
sampling is the method of choice unless (1) there
are known distinct strata; (2) one wants to prove or
disprove that there are distinct strata; or (3) one is
limited in the number of samples and desires to
minimize the size of a “hot spot” that could go
unsampled. If any of these conditions exist,
stratified random sampling would be the better
strategy.
This strategy, however, can be employed only if all
points within the pile can be accessed. In such
cases, the pile should be divided into a three-
dimensional grid system; the grid sections assigned
numbers; and the sampling points chosen using
random-number tables or random-number
generators. The only exceptions to this are
situations in which representative samples cannot be
collected safely or where the investigative team is
trying to determine worst-case conditions.
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If sampling is limited to certain portions of the pile,
a statistically based sample will be representative
only of that portion, unless the waste is
homogenous.
5.5 EQUIPMENT/APPARATUS
Waste pile solids indude powdered, granular, or
block materials of various sizes, shapes, structure,
and compactness. The type of sampler chosen
should be compatible with the waste. Samplers
commonly used for waste piles include: stainless
steel scoops, shovels, trowels, spoons, and stainless
steel hand augers, sampling triers, and grain
samplers.
Waste pile sampling equipment check list:
• sampling plan
• maps/plot plan
• safety equipment, as specified in the health
and safety plan
• compass
• tape measure
• survey stakes or flags
• camera and film
• stainless steel, plastic, or other appropriate
homogenization bucket or bowl
1-quart mason jars w/Teflon liners
Ziploc plastic bags
logbook
labels
chain of custody forms and seals
field data sheets
cooler(s)
ice
decontamination supplies/equipment
canvas or plastic sheet
spade or shovel
spatula
scoop
plastic or stainless steel spoons
trowel
continuous flight (screw) auger
bucket auger
post hole auger
extension rods
T-handle
thin-wall tube sampler
sampling trier
grain sampler
5.6 REAGENTS
No chemical reagents are used for the preservation
of waste pile samples; however, decontamination
solutions may be required. If decontamination of
equipment is required, refer to ERT Standard
Operating Procedure (SOP) #2006, Sampling
Equipment Decontamination, and the site-specific
work plan.
5.7 PROCEDURES
5.7.1 Preparation
1. Determine the extent of the sampling effort,
the sampling methods to be employed, and
which equipment and supplies are required.
2. Obtain necessary sampling and monitoring
equipment.
3. Decontaminate or predean equipment, and
ensure that it is in working order.
4. Prepare schedules, and coordinate with staff
client, and regulatory agencies, if appropriate.
5. Perform a general site survey prior to site entry
in accordance with the site-specific health and
safety plan.
6. Use stakes or flagging to identify and mark all
sampling locations. Specific site factors,
including extent and nature of contaminants,
should be considered when selecting sample
locations. If required, the proposed locations
may be adjusted based on site access, property
boundaries, and surface obstructions.
5.7.2 Sample Collection
SAMPLING WITH SHOVELS AND
SCOOPS
Collection of samples from surface portions of the
pile can be accomplished with tools such as spades,
shovels, and scoops. Surface material can be
removed to the required depth with this equipment,
then a stainless steel or plastic scoop can be used to
collect the sample.
Accurate, representative samples can be collected
with this procedure depending on the care and
•
•
•
•
•
•
•
•
•
S
S
•
S
S
•
S
S
S
S
•
•
•
26
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precision demonstrated by sample team members.
Use of a flat, pointed mason trowel to cut a block
of the desired material can be helpful when
undisturbed profiles are required. A stainless steel
scoop, lab spoon, or plastic spoon will suffice in
most other applications. Care should be exercised
to avoid the use of devices plated with chrome or
other materials. Plating is particularly common with
implements such as garden trowels.
Use the following procedure to coLlect surface
samples:
1. Carefully remove the top layer of material to
the desired sample depth with a precleaned
spade.
2. Using a precleaned stainless steel scoop, plastic
spoon, or trowel, remove and discard a thin
layer of material from the area which came in
contact with the spade.
3. If volatile organic analysis is to be performed,
transfer the sample into an appropriate, labeled
sample container with a stainless steel lab
spoon, plastic lab spoon, or equivalent and
secure the cap tightly. Place the remainder of
the sample into a stainless steel, plastic, or
other appropriate homogenization container,
and mix thoroughly to obtain a homogenous
sample representative of the entire sampling
interval. Then, either place the sample into
appropriate, labeled containers and secure the
caps tightly; or, if composite samples are to be
collected, place a sample from another
sampling interval into the homogenization
container and mix thoroughly. When
compositing is complete, place the sample into
appropriate, labeled containers and secure the
caps tightly.
SAMPLING WITH AUGERS AND THIN-
WALL TUBE SAMPLERS
This system consists of an auger, a series of
extensions, a “T” handle, and a thin-wall tube
sampler (Figure 13, Appendix B). The auger is
used to bore a hole to a desired sampling depth,
and is then withdrawn. The sample may be
collected directly from the auger. If a core sample
is to be collected, the auger tip is then replaced with
a thin-wall tube sampler. The system is then
lowered down the borehole, and driven into the pile
at the completion depth The system is withdrawn
and the core collected from the thin-wall tube
sampler.
Several augers arc available. These include:
bucket, continuous flight (screw), and post hole
augers. Bucket augers are better for direct sample
recovery since they provide a large volume of
sample in a short time. When continuous flight
augers are used, the sample can be collected
directly from the flights, which are usually at 5-foot
intervals. The continuous flight augers are
satisfactory for use when a composite of the
complete waste pile column is desired. Post hole
augers have limited utility for sample collection as
they are designed to cut through fibrous, rooted,
swampy areas.
Use the following procedure for collecting waste
pile samples with the auger:
1. Attach the auger bit to a drill rod extension,
and attach the “1’” handle to the drill rod.
2. Clear the area to be sampled of any surface
debris. It may be advisable to remove the first
3 to 6 inches of surface material for an area
approximately 6 inches in radius around the
drilling location.
3. Begin augering, periodically removing and
depositing accumulated materials onto a plastic
sheet spread near the hole. This prevents
accidental brushing of loose material back
down the borehole when removing the auger or
adding drill rods. It also facilitates refilling the
hole, and avoids possible contamination of the
surrounding area.
4. After reaching the desired depth, slowly and
carefully remove the auger from boring. When
sampling directly from the auger, collect sample
after the auger is removed from boring and
proceed to Step 10.
5. Remove auger tip from drill rods and replace
with a precleaned thin-wall tube sampler.
Install proper cutting tip.
6. Carefully lower the tube sampler down the
borehole. Gradually force the tube sampler
into the pile. Care should be taken to avoid
scraping the borehole sides. Avoid hammering
the drill rods to facilitate coring as the
vibrations may cause the boring walls to
collapse.
27
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7. Remove the tube sampler, and unscrew the drill
rods.
8. Remove the cutting tip and the core from
device.
9. Discard the top of the core (approximately 1-
inch), as this represents material collected
before penetration of the layer of concern.
Place the remaining core into the appropriate
labeled sample container. Sample
homogenization is not required.
10. If volatile organic analysis is to be performed,
transfer the sample into an appropriate, labeled
sample container with a stainless steel lab
spoon, plastic lab spoon, or equivalent and
secure the cap tightly. Place the remainder of
the sample into a stainless steel, plastic, or
other appropriate homogenization container,
and mix thoroughly to obtain a homogenous
sample representative of the entire sampling
interval. Then, either place the sample into
appropriate, labeled containers and secure the
caps tightly; or, if composite samples are to be
collected, place a sample from another
sampling interval into the homogenization
container and mix thoroughly. When
compositing is complete, place the sample into
appropriate, labeled containers and secure the
caps tightly.
11. If another sample is to be collected in the same
hole, but at a greater depth, reattach the auger
bit to the drill and assembly, and follow steps 3
through 11, making sure to decontaminate the
auger and tube sampler between samples.
SAMPLING WITH A TRIER
This system consists of a trier and a “V handle.
The auger is driven into the waste pile and used to
extract a core sample from the appropriate depth.
Use the following procedure to collect waste pile
samples with a sampling trier:
1. Insert the trier (Figure 14, Appendix B) into
the material to be sampled at a 0° to 45° angle
from horizontal. This orientation minimizes
spillage of the sample. Extraction of the
samples might require tilting of the sample
containers.
2. Rotate the trier once or twice to cut a core of
material.
3. Slowly withdraw the trier, making sure that the
slot is facing upward.
4. If volatile organic analysis is to be performed,
transfer the sample into an appropriate, labeled
sample container with a stainless steel lab
spoon, plastic lab spoon, or equivalent and
secure the cap tightly. Place the remainder of
the sample into a stainless steel, plastic, or
other appropriate homogenization container,
and mix thoroughly to obtain a homogenous
sample representative of the entire sampling
interval. Then, either place the sample into
appropriate, labeled containers and secure the
caps tightly; or, if composite samples are being
collected, place samples from the other
sampling intervals into the homogenization
container and mix thoroughly. When
compositing is complete, place the sample into
appropriate, labeled containers and secure the
caps tightly.
SAMPLING WITH A GRAIN SAMPLER
The grain sampler (Figure 15, Appendix B) is used
for sampling powdered or granular wastes or
materials in bags, fiberdrums, sacks, similar
containers or piles. This sampler is most useful
when the solids are no greater than 0.6 cm (1/4
inch) in diameter.
This sampler consists of two slotted telescoping
brass or stainless steel tubes. The outer tube has a
conical, pointed tip at one end that permits the
sampler to penetrate the material being sampled.
The sampler is opened and closed by rotating the
inner tube. Grain samplers are generally 61 to 100
cm (24 to 40 inch) long by 1.27 to 2.54 cm (1/2 to
1 inch) in diameter and are commercially available
at laboratory supply houses.
Use the following procedures to collect waste pile
samples with a grain sampler:
1. With the sampler in the closed position, insert
it into the granular or powdered material or
waste being sampled from a point near a top
edge or corner, through the center, and to a
point diagonally opposite the point of entry.
28
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2. Rotate the sampler inner tube into the open
position.
3. Wiggle the sampler a few times to allow
material to enter the open slots.
4 With the sampler in the closed position,
withdraw it from the material being sampled.
5. Place the sampler in a horizontal position with
the slots facing upward.
6. Rotate the outer tube and slide it away from
the inner tube.
7. If volatile organic analysis is to be performed,
transfer the sample into an appropriate, labeled
sample container with a stainless steel lab
spoon, plastic lab spoon, or equivalent and
secure the cap tightly. Place the remainder of
the sample into a stainless steel, plastic, or
other appropriate homogenization container,
and mix thoroughly to obtain a homogenous
sample representative of the entire sampling
interval. Then, either place the sample into
appropriate, labeled containers and secure the
caps tightly; or, if composite samples are to be
collected, place a sample from another
sampling interval into the homogenization
container and mix thoroughly. Whcn
conipositing is complete, place the sample into
appropriate, labeled containers and secure the
caps tightly.
5.8 CALCULATIONS
This section is not applicable to this SOP.
5.9 QUALITY ASSURANCE/
QUALITY CONTROL
There are no specific quality assurance activities
which apply to the implementation of these
procedures. However, the following QA procedures
apply:
• All data must be documented on field data
sheets or within site logbooks.
• All instrumentation must be operated in
accordance with operating instructions as
supplied by the manufacturer, unless
otherwise specified in the work plan.
Equipment checkout and calibration
activities must occur prior to
sampling/operation, and they must be
documented.
5.10 DATA VALIDATION
This section is not applicable to this SOP.
5.11 HEALTH AND SAFETY
When working with potentially hazardous materials,
follow U.S. EPA, OSHA and specific health and
safety procedures.
29
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APPENDIX A
Drum Data Sheet Form
31
-------
Drum Data Sheet Form
SOP #2009
Drum !D#: ________________________________ Date Sampled:
Estimated Liquid Quantity: _____________________ Time: _______________________
Grid Location: _________________________________
Staging Location: ___________________________
Sampler’s Name: _____________________________
Drum Condition: ____________________________
Sampling Device _____________________________
Physical Appearance of the Drum/Bulk Contents _____________________________________________________
Odor
Color:
pH _____________________________________ % Liquid:
Laboratory Date of Analysis:
Analytical Data. ____________________
Compatibility
Hazard: ___________________________
Waste ID. _________________________
Treatment Disposal Rccommcnd ttions
Approval
Lab
D .iit
Date.
Site
Manager
* Area of sde where drum was originally localed
Based on di Napoli, I )M2 Tahlc originally prinied in the Proceedings ol tti N,tii iul Conference on
Management of Uncoiii rolled I tj,’ardotis Waste Sites, I )S2 As ,iilahle Irom I l.wardous Nialeriak Control
Research ln i flute, 911X) Columli ,i Blvd , Silser Spring, Ml) 2(y) 10
-------
APPENDIX B
Figures
35
-------
Figure 1: Universal Bung Wrench
SOP #2009
36
-------
Figure 2: Drum Deheader
SOP #2009
37
-------
Figure 3: Hand Pick, Pickaxe, and Hand Spike
SOP #2009
HAND PICK
PICKAXE
HAND SPIKE
38
-------
Figure 4: Backhoe Spike
SOP #2009
39
-------
Figure 5: Hydraulic Drum Opener
SOP #2009
40
-------
Figure 6: Pneumatic Bung Remover
SOP #2009
41
-------
Figure 7: Glass Thief
SOP# 2009
Insert open tube (thief) sampler
in containerized liquid.
Remove open tube (thief) scmpler
from containerized liquid.
A )
Cover top of sampler with gloved
thumb.
4.
Place open tube samp’er over
appropriate sample bottle and
remove gloved thumb.
-7-
1.
42
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Figure 8: COLIWASA
SOP #2009
—j — 2.86 CM(1W)
I h nc4Le— H
n
___________ 17.8 cri(7’)
: °: ‘ 0
I I 6,35 cr <2 4’)
/ I I L 10.16 cM(4’)
Locking bLock
I I I I Pipe, PVC, translucent
I I I I 4.13 cm(1 ‘) I.D.,
I I I 4.26 cr,(1% ‘) CD.
I I I
II I I
I!
Ii I
I I I I
I l Stopper rod, PVC,
152 c (60’) I I 0.95 cm(3/8’) O.D.
I I
I I I
I I
II II
I I
I II
II II
I I I I
I II
II II
I I I
II I I
I I I
Stopper I I
Stopper, neoprene, #9, tapered,
I ______ 0.95 cri(3/8’) PVC lock nut
I ! and washer
SAMPLING POSITION CLOSED POSITION
43
-------
Figure 9: Bacon Bomb Sampler
SOP #2010
44
-------
Figure 10: Sludge Judge
SOP #2010
45
-------
Figure 11: Subsurface Grab Sampler
SOP #2010
46
-------
Figure 12: Bailer
SOP #2010
STAINLESS WIRE
CABLE
—1/4” O.D.X1”I.D.TEFLON
I EXTRUDED TUBING,
18 TO 36” LONG
3/4” DIAMETER
GLASS OR TEFLON
I I 1” DIAMETER TEFLON
EXTRUDED ROD
5/16” D;AM ER
HOLE
47
-------
Figure 13: Samp’ing Augers
SOP #2017
it II
TUBE BUCKET
AUGER AUGER
48
-------
Figure 14: Sampling Trier
SOP #2017
J1
L 1.27—2.54 c
(1/2”—1)
49
-------
Figure 15: Grain Sampler
SOP #2017
61—100 cm
(24—40)
uIi..- = 1.27—2 54 cm
I (1/2—1)
50
-------
APPENDIX C
Calculations
51
-------
Various Volume Calculations
SOP #2010
FLLIPTICAL C ONTAINFR
ANY RECTANGULAR CONTAINER
Total Volume
V 1/6 7TD =O.523498D
Partial Volume
V=1/3 i d 2 (3/2 0—a)
Total Volume
V= BDH
Partial Volume
V= Dh
TRiANGULAR CONTAINER
Total Volume
V=1/2 HBL
H
Case 1
Partial Volume
v=1/2 hBL
Case 2
Partial Volume
v=1/2 L(HB—hB)
h
-r
t
Total Volume
V=HLW
Partial Volume
V=hLW
RIGHT CYLINDER
1
Total Volume
v=1/4 D 2 H
Partial Volume
V=1/4iiD 2 h
SPHERE
52
-------
Various Volume Calculations (Cont’d)
FRUSTUM OF A CONE
CONE
Case 2
21
_ 0 _
Total ‘Iolume
‘1= iv/12 H(D 1 2 +01 0 2 +D 2 2 )
Partial Volume
V= rr/12 h(D 1 2 +01 d+d 2 )
Case 1
PARABOLIC CONTAINER
Case 2
Total Volume
V= /12 D H
Partial Volume Case 1
V= i’r/12.d 2 h
Partial Volume Case 2
v= ir/12(D 2 H—d 2 h)
ffBH
HBH
1
Case 1
Partial Volume
V=2/3 hdL
Case 2
PorUol Volume
V=2/3 (HD—hd).L
Case 1
H
HH
h
L
F 1
Total Volume
V=2/3 HOL
L
53
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References
Illuminating Engineers Society. 1984. IES Lighting Handbook. New York, NY. eds. John E. Kaufman and
Jack Christensen. (2 volumes).
National Institute for Safety and Health. October 1985. Occupational Safety and Health Guidance Manual for
Hazardous Waste Site Activities.
New Jersey Department of Environmental Protection, Division of Hazardous Site Mitigation. 1988. Field
Sampling Procedures Manual.
U.S. EPA. 1985. Guidance Document for Cleanup of Surface Tank and Drum Sites. OSWER Directive
9380.0-3. NTIS Ref: PB-87-110-72.
U.S. EPA. 1986. Drum Handling Practices at Hazardous Waste Sites. EPA/600/2-86/013.
U. S. EPA/Region IV, Environmental Services Division. April 1, 1986. Engineering Support Branch Standard
Operating Procedures and Quality Assurance Manual. Athens, Georgia.
U.S. EPA/OSWER. November, 1986. Test Methods for Evaluating Solid Waste, Third Edition, Vol. H, Field
Manual. EPA Docket SW-846.
U.S. EPA. 1987. A Compendium of Superfund Field Operations Methods. EPA/540/5-87/001. Office of
Emergency and Remedial Response. Washington, D.C. 20460.
) S Goverrunont PmiJng once l 1 — 9.8- 18114o582 55
-------
United Stat Center for Environmental Research BULK RATE
Environmentai Protection Information POSTAGE & FEES PAID
Agency Cincinnati OH ‘15268-1012 EPA
PERMIT No G-35
Official Business
Penalty for Private Use $300
EPA’540’P-91 ‘008
-------
United States
Environmentai ProtectOfl
Agency
Superfund
Office of Emergency and
Remedial Response
Washington DC 20460
Compendium of ERT
Soil Sampling
6EPA
-------
GENERAL FIELD
SAMPLING GUIDELINES
SOP#. 2001
DATE. 08/11/94
REV #‘00
1.0 SCOPE AND APPLICATION
The purpose of this Standard Operating Procedure
(SOP) is to provide general field sampling guidelmes
that will assist REAC personnel in choosing sampling
strategies, location, and frequency for proper
assessment of site characteristics This SOP is
applicable to all field activities that involve sampling
These are standard (i e, typically applicable)
operating procedures which may be varied or changed
as required, dependent on site conditions, equipment
lunitations or limitations imposed by the procedure In
all instances, the ultimate procedures employed should
be documented and associated with the final report
Mention of trade names or commercial products does
not constitute U S EPA endorsement or
recommendation for use
2.0 METHOD SUMMARY
Sampling is the selection of a representative portion of
a larger population, universe, or body Through
examination of a sample, the characteristics of the
larger body from which the sample was drawn can be
inferred In this manner, sampling can be a valuable
tool for determining the presence, type, and extent of
contamination by hazardous substances in the
environment
The primary objective of all sampling activities is to
characterize a hazardous waste site accurately so that
its impact on human health and the environment can
be properly evaluated It is only through sampling and
analysis that site hazards can be measured and the job
of cleanup and restoration can be accomplished
effectively with minimal risk The sampling itself
must be conducted so that every sample collected
retains its original physical form and chemical
composition In this way, sample integrity is insured,
quality assurance standards are maintained, and the
sample can accurately represent the larger body of
material under investigation
The extent to which valid inferences can be drawn
from a sample depends on the degree to which the
sampling effort conforms to the projects objectives
For example, as few as one sample may produce
adequate, technically valid data to address the
projects objectives Meeting the project’s objectives
requires thorough planning of sampling activities, and
implementation of the most appropriate sampling and
analytical procedures These issues will be discussed
in this procedure
3.0 SAMPLE PRESERVATION,
CONTAINERS, HANDLING,
AND STORAGE
The amount of sample to be collected, and the proper
sample container type (i e, glass, plastic), chemical
preservation, and storage requirements are dependent
on the matrix being sampled and the parameter(s) of
interest Sample preservation, containers, handling,
and storage for air and waste samples are discussed in
the specific SOPs for air and waste sampling
techniques
4.0 INTERFERENCES
POTENTIAL PROBLEMS
AND
The nature of the object or matenals being sampled
may be a potential problem to the sampler If a
matenal is homogeneous, it will generally have a
uniform composition throughout In this case, any
sample increment can be considered representative of
the material On the other hand, heterogeneous
samples present problems to the sampler because of
changes in the material over distance, both laterally
and vertically
Samples of hazardous materials may pose a safety
threat to both field and laboratory personnel Proper
health and safety precautions should be implemented
when handling this type of sample
-------
Environmental conditions, weather conditions, or
non-target chemicals may cause problems and/or
interferences when performing sampling activities or
when sampling for a specific parameter Refer to the
specific SOPs for sampling techniques
5,0 EQUIPMENT/APPARATUS
The equipment/apparatus required to collect samples
must be determined on a site specific basis Due to the
wide variety of sampling equipment available, refer to
the specific SOPs for sampling techniques which
include lists of the equipment/apparatus required for
sampling
6,0 REAGENTS
Reagents may be utilized for preservation of samples
and for decontamination of sampling equipment The
preservatives required are specified by the analysis to
be performed Decontamination solutions are
spec ified in ERT SOP #2006, Sampling Equipment
Decontamination
7.0 PROCEDURE
7.1 Types of Samples
In relation to the media to be sampled, two basic types
of samples can be considered the environmental
sample and the hazardous sample
Environmental samples are those collected from
streams, ponds, lakes, wells, and are off-site samples
that are not expected to be contaminated with
hazardous matenals They usually do not require the
special handling procedures typically used for
concentrated wastes However, in certain instances,
environmental samples can contain elevated
concentrations of pollutants and in such cases would
have to be handled as hazardous samples
Hazardous or concentrated samples are those collected
from drums, tanks, lagoons, pits, waste piles, fresh
spills, or areas previously identified as contaminated,
and require special handling procedures because of
their potential toxicity or hazard These samples can
be further subdivided based on their degree of hazard,
however, care should be taken when handling and
shipping any wastes believed to be concentrated
regardless of the degree
The importance of making the distinction between
environmental and hazardous samples is two-fold
(I) Personnel safety requirements Any sample
thought to contain enough hazardous
materials to pose a safety threat should be
designated as hazardous and handled in a
manner which ensures the safety of both field
and laboratory personnel
(2) Transportation requirements Hazardous
samples must be packaged, labeled, and
shipped according to the International Air
Transport Association (IATA) Dangerous
Goods Regulations or Department of
Transportation (DOT) regulations and U S
EPA guidelines
7.2 Sample Collection Techniques
In general, two basic types of sample collection
techmques are recognized, both of which can be used
for either environmental or hazardous samples
Grab Samples
A grab sample is defined as a discrete aliquot
representative of a specific location at a given point in
time The sample is collected all at once at one
particular point in the sample medium The
representativeness of such samples is defined by the
nature of the matenals being sampled In general, as
sources vary over time and distance, the
representativeness of grab samples will decrease
Composite Samples
Composites are nondiscrete samples composed of
more than one specific aliquot collected at vanous
sampling locations and/or different points in time
Analysis of this type of sample produces an average
value and can in certain instances be used as an
alternative to analyzing a number of individual grab
samples and calculating an average value It should
be noted, however, that compositing can mask
problems by diluting isolated concentrations of some
hazardous compounds below detection limits.
Compositing is often used for environmental samples
and may be used for hazardous samples under certain
conditions For example, compositing of hazardous
waste is often performed after compatibility tests have
2
-------
been completed to determine an average value over a
number of different locations (group of drums) This
procedure generates data that can be useful by
providing an average concentration within a number
of units, can serve to keep analytical costs down, and
can provide information useful to transporters and
waste disposal operations
For sampling situations involving hazardous wastes,
grab sampling techniques are generally preferred
because grab sampling minimizes the amount of time
sampling personnel must be in contact with the
wastes, reduces risks associated with compositing
unknowns, and eliminates chemical changes that
might occur due to compositing
7.3 Types of Sampling Strategies
The number of samples that should be collected and
analyzed depends on the objective of the investigation
There are three basic sampling strategies random,
systematic, and judgmental sampling
Random sampling involves collection of samples in a
nonsystematic fashion from the entire site or a specific
portion of a site Systematic sampling involves
coIlecti n of samples based Qfl a grid or a pattern
which has been previously established When
judgmental sampling is performed, samples are
collected only from the portion(s) of the site most
likely to be contaminated Often, a combination of
these strategies is the best approach depending on the
type of the suspectedilmown contamination, the
uniformity and size of the site, the leveiftype of
information desired, etc
7.4 QA Work Plans (QAWP)
A QAWP is required when it becomes evident that a
field investigation is necessary It should be initiated
in conjunction with, or immediately following,
notification of the field investigation This plan should
be clear and concise and should detail the following
basic components, with regard to sampling activities
C Objective and purpose of the investigation
C Basis upon which data will be evaluated
C Information known about the site including
location, type and size of the facility, and
length of operations/abandonment
C Type and volume of contaminated material,
contaminants of concern (including
concentration), and basis of the
information/data
C Technical approach including media/matrix
to be sampled, sampling equipment to be
used, sample equipment decontamination (if
necessary), sampling design and rationale,
and SOPs or description of the procedure to
be implemented
C Project management and reporting, schedule,
project organization and responsibilities,
manpower and cost projections, and required
deliverables
C QA objectives and protocols including tables
summarizing field sampling and QA/QC
analysis and objectives
Note that this list of QAW? components is not all-
inclusive and that additional elements may be added
or altered depending on the specific requirements of
the field investigation It should also be recognized
that although a detailed QAWP is quite important, it
may be impractical in some instances Emergency
responses and accidental spills are pnme examples of
such instances where time might prohibit the
development of site-specific QAWPs prior to field
activities In such cases, investigators would have to
rely on general guidelines and personal judgment, and
the sampling or response plans might simply be a
strategy based on preliminary information and
finalized on site In any event, a plan of action should
be developed, no matter how concise or informal, to
aid investigators in maintaining a logical and
consistent order to the implementation of their task
7.5 Legal Implications
The data derived from sampling activities are often
introduced as critical evidence during litigation of a
hazardous waste site cleanup Legal issues in which
sampling data are important may include cleanup cost
recovery, identification of pollution sources and
responsible parties, and technical validation of
remedial design methodologies Because of the
potential for involvement in legal actions, strict
adherence to technical and administrative SOPs is
essential during both the development and
implementation of sampling activities
Technically valid sampling begins with thorough
planning and continues through the sample collection
and analytical procedures Administrative
requirements involve thorough, accurate
3
-------
documentation of all sampling activities 10.0 DATA VALIDATION
Documentation requirements include maintenance of
a cham of custody, as well as accurate records of field Refer to the specific SOPs for data validation
activities and analytical instructions Failure to activities that are associated with sampling
observe these procedures fully and consistently may techniques
result in data that are questionable, invalid and
non-defensible in court, and the consequent loss of 11.0 HEALTH AND SAFETY
enforcement proceedings
When working with potentially hazardous materials,
8.0 CALCULATIONS follow U S EPA, OSHA, and corporate health and
safety procedures
Refer to the specific SOPs for any calculations which
are associated with sampling techniques
9.0 QUALITY ASSURANCE/
QUALITY CONTROL
Refer to the specific SOPs for the type and frequency
of QA/QC samples to be analyzed, the acceptance
criteria for the QAJQC saniples, and any other QA/QC
activities - which are associated with sampling
techniques
4
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SAMPLING EQUIPMENT
DECONTAMINATION
SOP#. 2006
DATE. 08/11/94
REV.#.00
1.0 SCOPE AND APPLICATION
The purpose of this Standard Operating Procedure
(SOP) is to provide a descnption of the methods used
for preventing, minimizing, or limiting
cross-contamination of samples due to inappropriate
or inadequate equipment decontamination and to
provide general guidelines for developing
decontamination procedures for sampling equipment
to be used during hazardous waste operations as per
29 Code of Federal Regulations (CFR) 1910 120
This SOP does not address personnel
decontamination
These are standard (i e typically applicable) operating
procedures which may be varied or changed as
required, dependent upon site conditions, equipment
limitation, or limitations imposed by the procedure
In all instances, the ultimate procedures employed
should be documented and associated with the final
report.
Mention of trade names or commercial products does
not constitute U S Environmental Protection Agency
(U S EPA) endorsement or recommendation for use
2.0 METHOD SUMMARY
Removing or neutralizing contaminants from
equipment minimizes the likelihood of sample cross
contamination, reduces or eliminates transfer of
contaminants to clean areas, and prevents the mixing
of incompatible substances
Gross contamination can be removed by physical
decontamination procedures These abrasive and
non-abrasive methods include the use of brushes, air
and wet blasting, and high and low pressure water
cleaning
The first step, a soap and water wash, removes all
visible particulate matter and residual oils and grease
This may be preceded by a steam or high pressure
water wash to facilitate residuals removal The
second step involves a tap water rinse and a
distilled/deionized water rinse to remove the
detergent An acid nnse provides a low pH media for
trace metals removal and is included in the
decontamination process if metal samples are to be
collected Itis followed by another distilled/deionized
water rinse If sample analysis does not include
metals, the acid rinse step can be omitted Next, a
high purity solvent rinse is performed for trace
organics removal if organics are a concern at the site
Typical solvents used for removal of organic
contaminants include acetone, hexane, or water
Acetone is typically chosen because it is an excellent
solvent, miscible in water, and not a target analyte on
the Priority Pollutant List If acetone is known to be
a contaminant of concern at a given site or if Target
Compound List analysis (which includes acetone) is
to be performed, another solvent may be substituted
The solvent must be allowed to evaporate completely
and then a final distilled/deionized water nnse is
performed This rinse removes any residual traces of
the solvent
The decontamination procedure described above may
be summarized as follows
Physical removal
2
3
4
5
6
7
8
9.
Non-phosphate detergent wash
Tap water rinse
Distilled/deionized water rinse
10% nitnc acid rinse
Distilled/deionized water rinse
Solvent rinse (pesticide grade)
Air dry
Distilled/deionized water rinse
If a particular contaminant fraction is not present at
the site, the nine (9) step decontamination procedure
specified above may be modified for site specificity
For example, the nitnc acid rinse may be eliminated
if metals are not of concern at a site Similarly, the
solvent rinse may be eliminated if organics are not of
1
-------
concern at a site Modifications to the standard
procedure should be documented in the site specific
work plan or subsequent report
3.0 SAMPLE PRESERVATION,
CONTAINERS, HANDLING,
AND STORAGE
The amount of sample to be collected and the proper
sample container type (i a, glass, plastic), chemical
preservation, and storage requirements are dependent
on the matrix being sampled and the parameter(s) of
interest.
More specifically, sample collection and analysis of
decontamination waste may be required before
beginning proper disposal of decontamination liquids
and solids generated at a site This should be
determined prior to initiation of site activities
4.0 INTERFERENCES
POTENTIAL PROBLEMS
AND
C The use of distilled/deionized water
commonly available from commercial
vendors may be acceptable for
decontamination of sampling equipment
provided that it has been verified by
laboratory analysis to be analyte free
(specifically for the contaminants of
concern)
C The use of an untreated potable water supply
is not an acceptable substitute for tap water
Tap water may be used from any municipal
or industrial water treatment system
C If acids or solvents are utilized in
decontamination they raise health and safety,
and waste disposal concerns
C Damage can be incurred by acid and solvent
washing of complex and sophisticated
sampling equipment
5.0 EQUIPMENT/APPARATUS
Decontamination equipment, materials, and supplies
are generally selected based on availability Other
considerations include the ease of decontaminating or
disposing of the equipment Most equipment and
supplies can be easily procured. For example, soft-
bristle scrub brushes or long-handled bottle brushes
can be used to remove contaminants Large
galvanized wash tubs, stock tanks, or buckets can hold
wash and rinse solutions Children’s wadmg pools can
also be used Large plastic garbage cans or other
similar containers lined with plastic bags can help
segregate contaminated equipment Contaminated
liquid can be stored temporarily in metal or plastic
cans or drums
The following standard materials and equipment are
recommended for decontamination activities
5.1 Decontamination Solutions
C Non-phosphate detergent
C Selected solvents (acetone, hexane, nitric
acid, etc)
C Tap water
C Distilled or deionized water
5.2 Decontamination Tools/Supplies
C Long and short handled brushes
C Bottle brushes
C Drop cloth/plastic sheeting
C Paper towels
C Plastic or galvanized tubs or buckets
C Pressurized sprayers (I-l O)
C Solvent sprayers
C Aluminum foil
5.3 Health and Safety Equipment
Appropnate personal protective equipment (i e, safety
glasses or splash shield, appropriate gloves, aprons or
coveralls, respirator, emergency eye wash)
5.4 Waste Disposal
C Trash bags
C Trash containers
C 55-gallon drums
C Metal/plastic buckets/containers for storage
and disposal of decontamination solutions
6.0 REAGENTS
There are no reagents used in this procedure aside
from the actual decontamination solutions Table I
(Appendix A) lists solvent rinses which may be
required for elimination of particular chemicals In
2
-------
general, the following solvents are typically utilized
for decontamination purposes
C lO% nitric acid is typically used for
inorganic compounds such as metals An
acid rinse may not be required if inorganics
are not a contaminant of concern
C Acetone (pesticide grade) ’
C Hexane (pesticide grade)t 1 )
C Methanol °
- Only if sample is to be analyzed for organics
7.0 PROCEDURES
As part of the health and safety plan, a
decontamination plan should be developed and
reviewed The decontamination line should be set up
before any personnel or equipment enter the areas of
potential exposure. The equipment decontamination
plan should include’
C The number, location, and layout of
decontamination stations
C Decontamination equipment needed
C Appropriate decontamination methods
C Methods for disposal of contaminated
clothing, equipment, and solutions
C Procedures can be established to minimize
the potential for contamination This may
include (I) work practices that minimize
contact with potential contaminants, (2)
using remote sampling techniques, (3)
covering monitoring and sampling equipment
with plastic, aluminum foil, or other
protective material, (4) watering down dusty
areas, (5) avoiding laying down equipment in
areas of obvious contamination, and (6) use
of disposable sampling equipment
7.1 Decontamination Methods
All samples and eqwpment leaving the contaminated
area of a site must be decontaminated to remove any
contamination that may have adhered to equipment
Various decontamination methods will remove
contaminants by’ (1) flushing or other physical
action, or (2) chemical complexing to inactivate
contaminants by neutralization, chemical reaction,
disinfection, or sterilization
Physical decontamination techniques can be grouped
into two categories abrasive methods and
non-abrasive methods, as follows
7. 1,1 Abrasive Cleaning Methods
Abrasive cleaning methods work by rubbing and
wearing away the top layer of the surface containing
the contaminant The mechanical abrasive cleaning
methods are most commonly used at hazardous waste
sites The following abrasive methods are available
Mechanical
Mechanical methods of decontamination include using
metal or nylon brushes The amount and type of
contaminants removed will vary with the hardness of
bristles, length of time brushed, degree of brush
contact, degree of contamination, nature of the surface
being cleaned, and degree of contaminant adherence
to the surface
Air Blasting
Air blasting equipment uses compressed air to force
abrasive material through a nozzle at high velocities
The distance between nozzle and surface cleaned, air
pressure, time of application, and angle at which the
abrasive strikes the surface will dictate cleaning
efficiency Disadvantages of this method are the
inability to control the amount of matenal removed
and the large amount of waste generated
Wet BIastin
Wet blast cleaning involves use of a suspended fine
abrasive. The abrasive/water mixture is delivered by
compressed air to the contaminated area By using a
very fine abrasive, the amount of materials removed
can be carefully controlled
7.1 2 Non-Abrasive Cleaning Methods
Non-abrasive cleaning methods work by forcing the
contaminant off a surface with pressure In general.
the equipment surface is not removed using
non-abrasive methods
3
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Low-Pressure Water
This method consists of a container which is filled
with water The user pumps air out of the container to
create a vacuum A slender nozzle and hose allow the
user to spray in hard-to-reach places
Hinh-Pressure Water
This method consists of a high-pressure pump, an
operator controlled directional nozzle, and a high-
pressure hose. Operating pressure usually ranges
from 340 to 680 atmospheres (atm) and flow rates
usually range from 20 to 140 liters per minute
Ultra-Hiah-Pressure Water
This system produces a water jet that is pressured
from 1,000 to 4,000 atmospheres This
ultra-high-pressure spray can remove tightly-adhered
surface films The water velocity ranges from 500
meters/second (m/s) (1,000 atm) to 900 rn/s (4,000
atm). Additives can be used to enhance the cleaning
action
Rinsing
Contaminants are removed by nnsing through
dilution, physical attraction, and solubihzation
Damt Cloth Removal
In some instances, due to sensitive, non-waterproof
equipment or due to the unlikelihood of equipment
being contaminated, it is not necessary to conduct an
extensive decontamination procedure For example,
air sampling pumps hooked on a fence, placed on a
drum, or wrapped in plastic bags are not likely to
become heavily contaminated A damp cloth should
be used to wipe off contaminants which may have
adhered to equipment through airborne contaminants
or from surfaces upon which the equipment was set
Disinfection/Stenlization
Disinfectants are a practical means of inactivating
infectious agents Unfortunately, standard
sterilization methods are impractical for large
equipment This method of decontamination is
typically performed off-site
7.2 Field Sampling Equipment
Decontamination Procedures
The decontamination line is setup so that the first
station is used to clean the most contaminated item
It progresses to the last station where the least
contaminated item is cleaned The spread of
contaminants is further reduced by separating each
decontamination station by a minimum of three (3)
feet ldeally,the contamination should decrease as the
equipment progresses from one station to another
farther along in the line
A site is typically divided up into the following
boundaries. Hot Zone or Exclusion Zone (EZ), the
Contamination Reduction Zone (CR1), and the
Support or Safe Zone (SZ) The decontamination line
should be setup in the Contamination Reduction
Comdor (CRC) which is in the CRZ Figure 1
(Appendix B) shows a typical contaminant reduction
zone layout The CRC controls access into and out of
the exclusion zone and confines decontamination
activities to a limited area The CRC boundaries
should be conspicuously marked The far end is the
hotline, the boundary between the exclusion zone and
the contamination reduction zone The size of the
decontamination comdor depends on the number of
stations in the decontamination process, overall
dimensions of the work zones, and amount of space
available at the site Whenever possible, it should be
a straight line
Anyone in the CRC should be wearing the level of
protection designated for the decontamination crew
Another comdor may be required for the entry and
exit of heavy equipment Sampling and monitoring
equipment and sampling supplies are all maintained
outside of the CRC Personnel don their equipment
away from the CRC and enter the exclusion zone
through a separate access control point at the hotime
One person (or more) dedicated to decontaminating
equipment is recommended
7,2 1 Decontamination Setup
Starting with the most contaminated station, the
decontamination setup should be as follows
Station I Se re2ate Ecruinment Dron
Place plastic sheeting on the ground (Figure 2,
Appendix B) Size will depend on amount of
4
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equipment to be decontaminated Provide containers
lined with plastic if equipment is to be segregated
Segregation may be required if sensitive equipment or
mildly contaminated equipment is used at the same
time as equipment which is likely to be heavily
contaminated
Station 2 Physical Removal With A High-Pressure
Washer (Optionafl
As indicated in 7 I 2, a high-pressure wash may be
required for compounds which are difficult to remove
by washing with brushes The elevated temperature of
the water from the high-pressure washers is excellent
at removing greasy/oily compounds High pressure
washers require water and electricity.
poo 1 with tap water Several bottle and bristle brushes
should be dedicated to this station Approximately
10-50 gallons of water may be required initially
depending upon the amount of equipment to
decontaminate and the amount of gross contamination
Station 5 Low-Pressure S ravers
Fill a low-pressure sprayer with distilled/deionized
water Provide a 5-gallon bucket or basin to contain
the water during the rinsing process Approximately
10-20 gallons of water may be required initially
depending upon the amount of equipment to
decontaminate and the amount of gross contamination
Station 6 Nitric Acid Sprayers
A decontamination pad may be required for the high-
pressure wash area An example of a wash pad may
consist of an approximately 1 1/2 foot-deep basin
lined wflh plastic sheeting and sloped to a sump at one
corner A layer of sand can be placed over the plastic
and the basin is filled with gravel or shell The sump
is also lined with visqueen and a barrel is placed in the
hole to prevent collapse A sump pump is used to
remove the water from the sump for transfer into a
drum
Typically heavy machinery is decontaminated at the
end of the day unless site sampling requires that the
machinery be decontaminated frequently A separate
decontamination pad may be required for heavy
equipment
Station 3 Physical Removal With Brushes And A
Wash Basin
Prior to setting up Station 3, place plastic sheeting on
the ground to cover areas under Station 3 through
Station 10.
Fill a wash basin, a large bucket, or child’s swimming
pool with non-phosphate detergent and tap water
Several bottle and bristle brushes to physically remove
contamination should be dedicated to this station
Approximately 10 - 50 gallons of water may be
required initially depending upon the amount of
equipment to decontaminate and the amount of gross
contamination
Fill a spray bottle with 10% nitric acid An acid rinse
may not be required if inorganics are not a
contaminant of concern The amount of acid will
depend on the amount of equipment to be
decontaminated Provide a 5-gallon bucket or basin to
collect acid during the rinsing process
Station 7 Low-Pressure Sprayers
Fill a low-pressure sprayer with distilled/deionized
water Provide a 5-gallon bucket or basin to collect
water during the rinsate process
Station 8 Organic Solvent Sprayers
Fill a spray bottle with an organic solvent Alter each
solvent rinse, the equipment should be rinsed with
distilled/deionized water and air dried Amount of
solvent will depend on the amount of equipment to
decontaminate Provide a 5-gallon bucket or basin to
collect the solvent during the rinsing process
Solvent rinses may not be required unless organics are
a contaminant of concern, and may be eliminated from
the station sequence
Station 9 Low-Pressure Sprayers
Fill a low-pressure sprayer with distilled/deionized
water Provide a 5-gallon bucket or basin to collect
water during the rinsate process
Station 4 Water Basin
Station 10 Clean Equipment Drop
Fill a wash basin, a large bucket, or child’s swimming
Lay a clean piece of plastic sheeting over the bottom
5
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plastic layer This will allow easy removal of the
plastic in the event that it becomes dirty Provide
aluminum foil, plastic, or other protective material to
wrap clean equipment
7.2 2 Decontamination Procedures
Station I Segregate Equipment Drop
Deposit equipment used on-site Ci e , tools, sampling
devices and containers, monitoring instruments radios,
clipboards, etc.) on the plastic drop cloth/sheet or in
different containers with plastic liners Each will be
contaxninated to a different degree Segregation at the
drop reduces the probability of cross contamination
Loose leaf sampling data sheets or maps can be placed
in plastic zip lock bags if contamination is evident
Station 2 Physical Removal With A High-Pressure
Washer (Optional )
Use high pressure wash on grossly contaminated
equipment. Do not use high- pressure wash on
sensitive or non-waterproof equipment
Station 3 Physical Removal With Brushes And A
Wash Basin
Using a spray bottle rinse sanipling equipment with
nitric acid Begin spraying (inside and outside) at one
end of the equipment allowing the acid to drip to the
other end into a 5-gallon bucket A rinsate blank may
be required at this station Refer to Section 9
Station 7 Low-Pressure Sprayers
Rinse sampling equipment with distilled/deionized
water with a low-pressure sprayer
Station 8 Organic Solvent Sprayers
Rinse sampling equipment with a solvent Begin
spraying (inside and outside) at one end of the
equipment allowing the solvent to drip to the other
end into a 5-gallon bucket Allow the solvent to
evaporate from the equipment before going to the next
station A QC nnsate sample may be required at this
station
Station 9 Low-Pressure Sprayers
Rinse sampling equipment with distilled/deionized
water with a low-pressure washer
Station 10 Clean Equipment Drop
Scrub equipment with soap and water using bottle and
bristle brushes Only sensitive equipment (i e., radios,
air monitoring and sampling equipment) which is
waterproof should be washed. Equipment which is
not waterproof should have plastic bags removed and
wiped down with a damp cloth Acids and organic
rinses may also rum sensitive equipment. Consult the
manufacturers for recommended decontamination
solutions
Station 4 Equipment Rinse
Wash soap off of equipment with water by immersing
the equipment in the water while brushing Repeat as
many times as necessary.
Station 5 Low-Pressure Rinse
Rinse sampling equipment with distilled/deionized
water with a low-pressure sprayer.
Station 6 Nitric Acid Sprayers ( required only if
metals are a contaminant of concern )
Lay clean equipment on plastic sheeting Once air
dried, wrap sampling equipment with aluminum foil,
plastic, or other protective matenal
7.2 3 Post Decontamination Procedures
Collect high-pressure pad and heavy
equipment decontamination area liquid and
waste and store in appropriate drum or
container A sump pump can aid in the
collection process Refer to the Department
of Transportation (DOT) requirements for
appropriate containers based on the
contaminant of concern
2 Collect high-pressure pad and heavy
equipment decontamination area solid waste
and store in appropriate drum or container
Refer to the DOT requirements for
appropriate containers based on the
contaminant of concern
3 Empty soap and water liquid wastes from
basins and buckets and store in appropriate
6
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drum or container Refer to the DOT
requirements for appropriate containers
based on the contaminant of concern
4 Empty acid rinse waste and place in
appropriate container or neutralize with a
base and place m appropriate drum pH
paper or an equivalent pH test is required for
neutralization Consult DOT requirements
for appropriate drum for acid rinse waste
5 Empty solvent nnse sprayer and solvent
waste into an appropriate container Consult
DOT requirements for appropriate drum for
solvent nnse waste
6 Using low-pressure sprayers, nnse basins,
and brushes Place liquid generated from
this process into the wash water rinse
container
7 Empty low-pressure sprayer water onto the
ground
8 Place all solid waste materials generated
from the decontamination area (i e, gloves
and plastic sheeting, etc) in an approved
DOT drum Refer to the DOT requirements
for appropnate containers based on the
contaminant of concern
9 Wnte appropriate labels for waste and make
arrangements for disposal. Consult DOT
regulations for the appropnate label for each
drum generated from the decontamination
process
8.0 CALCULATIONS
This section is not applicable to this SOP
9.0 QUALITYASSURANCE/
QUALITY CONTROL
A rinsate blank is one specific type of quality control
sample associated with the field decontamination
process This sample will provide information on the
effectiveness of the decontamination process
employed in the field
Rinsate blanks are samples obtained by running
analyte free water over decontaminated sampling
equipment to test for residual contamination The
blank water is collected in sample containers for
handling, shipment, and analysis These samples are
treated identical to samples collected that day A
rinsate blank is used to assess cross contamination
brought about by improper decontamination
procedures Where dedicated sampling equipment is
not utilized, collect one rinsate blank per day per type
of sampling device samples to meet QA2 and QA3
objectives
If sampling equipment requires the use of plastic
tubing it should be disposed of as contaminated and
replaced with clean tubing before additional sampling
occurs
10.0 DATA VALIDATION
Results of quality control samples will be evaluated
for contamination This information will be utilized
to qualify the environmental sample results in
accordance with the project’s data quality objectives
11.0 HEALTH AND SAFETY
When working with potentially hazardous materials,
follow OSHA, U S EPA, corporate, and other
applicable health and safety procedures
Decontamination can pose hazards under certain
circumstances Hazardous substances may be
incompatible with decontamination materials For
example, the decontamination solution may react with
contaminants to produce heat, explosion, or toxic
products Also, vapors from decontamination
solutions may pose a direct health hazard to workers
by inhalation, contact, fire, or explosion
The decontamination solutions must be determined to
be acceptable before use Decontamination materials
may degrade protective clothing or equipment, some
solvents can permeate protective clothing If
decontamination materials do pose a health hazard,
measures should be taken to protect personnel or
substitutions should be made to eliminate the hazard
The choice of respiratory protection based on
contaminants of concern from the site may not be
appropriate for solvents used in the decontamination
process
Safety considerations should be addressed when using
abrasive and non-abrasive decontamination
7
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equipment Maximum air pressure produced by 12.0 REFERENCES
abrasive equipment could cause physical injury
Displaced material requires control mechanisms Field Sampling Procedures Manual, New Jersey
Department of Environmental Protection, Februaiy,
Material generated from decontamination activities 1988
requires proper handling, storage, and disposal
Personal Protective Equipment may be required for A Compendium of Superfund Field Operations
these activities Methods, EPA 54OIp-8 7 IOO1
Material safety data sheets are required for all Engineering Support Branch Standard Operating
decontamination solvents or solutions as required by Procedures and Quality Assurance Manual, USEPA
the Hazard Communication Standard (i e, acetone, Region IV, April 1, 1986
alcohol, and tnsodlu!nphosphate)
Guidelines for the Selection of Chemical Protective
In some jurisdictions, phosphate containing detergents Clothing, Volume I, Third Edition, American
(i.e., TSP) are banned Conference of Governmental Industrial Hygienists,
Inc ,February, 1987
Occupational Safety and Health Guidance Manual for
Hazardous Waste Site Activities,
NIOSH/OSHAIUSCG/EPA, October, 1985
8
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APPENDIX A
Table
Table 1 Soluble Contaminants and Recommended Solvent Rinse
TABLE 1
Soluble Contaminants and Recommended Solvent Rinse
SOLVENTW
EXAMPLES OF
SOLVENTS
SOLUBLE
CONTAMINANTS
Water
—
Deionized water
Tap water
Low-chain hydrocarbons
Inorganic compounds
Salts
Some organic acids and other polar
compounds
Dilute Acids
Nitric acid
Acetic acid
Boric acid
Basic (caustic) compounds (e.g., amines
and hydrazines)
Dilute Bases
Sodium bicarbonate (e g,
soap deterg nt)
Acidic compounds
Phenol
Thiols
Some nitro and sulfonic compounds
Organic Solvents (2)
Alcohols
Ethers
Ketones
Aromatics
Straight chain alkalines
(e.g,
hexane)
Common petroleum
products (e.g, fuel, oil,
kerosene)
Nonpolar compounds (e g., some
organic compounds)
OrgarncSolvent
Hexane
PCBs
-
- Matenal safety data sheets are required for all decontamination solvents or solutions as require
by the Hazard Communication Standard
(2) - WARNING: Some organic solvents can permeate and/or degrade the protective clothing
9
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APPENDIX B
Figures
Figure 1 Contamination Reduction Zone Layout
EX’ ‘ QN
MZAW tOtWUDfl
o(eosnAMPumw
A A
- ® p — - - ——D— C
CCNTA
rt DtD - ‘-—u-kr — -1 Lrlr-3--: -
MO i(ITOIING
£OU 1PWLNT
SUPPLY_AItA _____
LZC ND
HOTLINE
COWTAl IINATION CONTROL UNE
•i ACCESS CONTROL POINT—ENTRANCE
:: ACCESS CONTROL POINT—EXIT
10
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APPENDIX B (Cont’d.)
Figures
Figure 2 Decontamination Layout
a
WA 4 SASIN WITh SOAP
AND TAP WATER
midSt SASili wiTh TAP WATt s
LOW P 1URt SPRAYER
Wmd DItTILL WATER
NTT C ACID 5Pt&flR
( Y NOT SE IEOUmCD)
ORGANIC SOLVENT SPRAYER
(UAY NOT K REOIJ1RED)
LOW PRESSURE SPRAYER
WITH DltflU.ED WATER
hU.Y NOT SE RtOU1 )
CLEAN LQUIPNENT DROP
LECLVD
• - HOTLINE
• : CONTAUINATIOH CONTROL UPIE
• PLASTIC SHEETING
L OVERLAPPING PLASTiC SHEETING
HEAVY COUIPIIENT
OCCONTAT1O I
AREA
2
0
U
LOW PRESSURE SPRAYER
WITH Dt!T1UID WATER
(NAY NOT SE REQUIRED)
II
11
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SOIL SAMPLING
SOP#: 2012
DATE 11/16/94
REV.#00
1.0 SCOPE AND APPLICATION
The purpose of this standard operating procedure
(SOP) is to describe the procedures for the collection
of representative soil samples Analysis of soil
samples may determine whether concentrations of
specific pollutants exceed established action levels, or
if the concentrations of pollutants present a risk to
public health, welfare, or the environment
These are standard (i e , typically applicable)
operating procedures which may be varied or changed
as requifed, dependent upon site conditions,
equipment limitations or limitations imposed by the
procedure In all instances, the ultimate procedures
employed should be documented and associated with
the final report.
Mention of trade names or commercial products does
not constitute U S Environmental Protection Agency
(EPA) endorsement or recommendation for use
2.0 METHOD SUMMARY
Soil samples may be collected using a variety of
methods and equipment The methods and equipment
used are dependent on the depth of the desired sample,
the type of sample required (disturbed vs
undisturbed), and the soil type Near-surface soils
may be easily sampled using a spade, trowel, and
scoop Sampling at greater depths may be performed
using a hand auger, continuous flight auger, a trier, a
split-spoon, or, if required, a backhoe
3.0 SAMPLE PRESERVATION,
CONTAINERS, HANDLING,
AND STORAGE
Chemical preservation of solids is not generally
recommended Samples should, however, be cooled
and protected from sunlight to minimize any potential
reaction
4.0 INTERFERENCES AND
POTENTIAL PROBLEMS
There are two primary interferences or potential
problems associated with soil sampling These
include cross contamination of samples and improper
sample collection Cross contamination problems can
be eliminated or minimized through the use of
dedicated sampling equipment If this is not possible
or practical, then decontamination of sampling
equipment is necessary Improper sample collection
can involve using contaminated equipment,
disturbance of the matrix resulting in compaction of
the sample or inadequate homogenization of the
samples where required, resulting in variable, non-
representative results
5.0 EQUIPMENT/APPARATUS
Soil sampling equipment includes the following
C Sampling plan
C Maps/plot plan
C Safety equipment, as specified in the Health
and Safety Plan
C Survey equipment
C Tape measure
C Survey stakes or flags
C Camera and film
C Stainless steel, plastic, or other appropriate
homogenization bucket, bowl or pan
Appropriate size sample containers
Ziplock plastic bags
Logbook
Labels
Chain of Custody records and seals
Field data sheets
Cooler(s)
Ice
Vermiculite
Decontamination supplies/equipment
Canvas or plastic sheet
Spade or shovel
C
C
C
C
C
C
C
C
C
C
C
C
-------
C Spatula
C Scoop
C Plastic or stainless steel spoons
C Trowel
C Continuous flight (screw) auger
C Bucket auger
C Post hole auger
C Extension rods
C T-handle
C Sampling trier
C Thin wall tube sampler
C Split spoons
C Vehimeyer soil sampler outfit
- Tubes
• Points
- Drive head
- Drop hammer
- Puller jack and grip
C Backhoe
6.0 REAGENTS
Reagents are not used for the preservation of soil
samples Decontamination solutions are specified in
the Sampling Equipment Decontamination SOP and
the site specific work plan
7.0 PROCEDURES
7.1 Preparation
Determine the extent of the sampling effort,
the sampling methods to be employed, and
the types and amounts of equipment and
supplies required
2 Obtain necessary sampling and monitoring
equipment
3 Decontaminate or pre-clean equipment, and
ensure that it is in working order
4 Prepare schedules, and coordinate with staff,
client, and regulatory agencies, if
appropriate.
5 Perform a general site survey prior to site
entry in accordance with the site specific
Health and Safety Plan
6 Use stakes, flagging, or buoys to identify and
mark all sampling locations Specific site
factors, including extent and nature of
contaminant should be considered when
selecting sample location If required, the
proposed locations may be adjusted based on
site access, property boundaries, and surface
obstructions All staked locations will be
utility-cleared by the property owner prior to
soil sampling
7.2 Sample Collection
7 2 1 Surface Soil Samples
Collection of samples from near-surface soil can be
accomplished with tools such as spades, shovels,
trowels, and scoops Surface material can be removed
to the required depth with this equipment, then a
stainless steel or plastic scoop can be used to collect
the sample
This method can be used in most soil types but is
limited to sampling near surface areas Accurate,
representative samples can be collected with this
procedure depending on the care and precision
demonstrated by the sample team member A
stainless steel scoop, lab spoon, or plastic spoon will
suffice in most other applications The use of a flat,
pointed mason trowel to cut a block of the desired soil
can be helpful when undisturbed profiles are required
Care should be exercised to avoid use of devices
plated with chrome or other materials Plating is
particularly common with garden implements such as
potting trowels
The following procedure is used to collect surface soil
samples
Carefully remove the top layer of soil or
debris to the desired sample depth with a pre-
cleaned spade
2 Using a pre-cleaned, stainless steel scoop,
plastic spoon, or trowel, remove and discard
a thin layer of soil from the area which came
in contact with the spade
3 If volatile organic analysis is to be
performed, transfer the sample directly into
an appropriate, labeled sample container with
a stainless steel lab spoon, or equivalent and
secure the cap tightly Place the remainder
of the sample into a stainless steel, plastic, or
-------
other appropriate homogenization container,
and mix thoroughly to obtain a homogenous
sample representative of the entire sampling
interval Then, either place the sample into
appropnate, labeled containers and secure the
caps tightly, or, if composite samples are to
be collected, place a sample from another
sampling interval or location into the
homogenization container and mix
thoroughly When compositing is complete,
place the sample into appropnate, labeled
containers and secure the caps tightly.
7.2.2 Sampling at Depth with Augers and
Thin Wall Tube Samplers
This system consists of an auger, or a thin-wall tube
sampler, a series of extensions, and a “T’ handle
(Figure 1, Appendix A) The auger is used to bore a
hole to a desired sampling depth, and is then
withdrawn. The sample may be collected directly
from the auger If a core sample is to be collected, the
auger tip is then replaced with a thin wall tube
sampler The system is then lowered down the
borehole, and driven into the soil to the completion
depth The system is withdrawn and the core is
collected from the thin wall tube sampler
Several types of augers are available, these include.
bucket type, continuous flight (screw), and post-hole
augers Bucket type augers are better for direct
sample recovery since they provide a large volume of
sample in a short time When continuous flight augers
are used, the sample can be collected directly from the
flights The continuous flight augers are satisfactory
for use when a composite of the complete soil column
is desired Post-hole augers have limited utility for
sample collection as they are designed to cut through
fibrous, rooted, swampy soil and cannot be used
below a depth of three feet
The following procedure will be used for collecting
soil samples with the auger
Attach the auger bit to a drill rod extension,
and attach the “T” handle to the drill rod
2 Clear the area to be sampled of any surface
debris (e g, twigs, rocks, litter) It may be
advisable to remove the first three to six
inches of surface soil for an area
approximately six inches in radius around the
drilling location
3 Begin augering, periodically removing and
depositing accumulated soils onto a plastic
sheet spread near the hole This prevents
accidental brushing of loose material back
down the borehole when removing the auger
or adding drill rods It also facilitates
refilling the hole, and avoids possible
contamination of the surrounding area
4 After reaching the desired depth, slowly and
carefully remove the auger from boring
When sampling directly from the auger,
collect the sample after the auger is removed
from the boring and proceed to Step 10
5 Remove auger tip from dnll rods and replace
with a pre-cleaned thin wall tube sampler
Install the proper cutting tip
6 Carefully lower the tube sampler down the
borehole Gradually force the tube
samplennto soil Care should be taken to
avoid scraping the borehole sides Avoid
hammering the drill rods to facilitate coring
as the vibrations may cause the boring walls
to collapse
7 Remove the tube sampler, and unscrew the
drill rods
S Remove the cutting tip and the core from the
device
9 Discard the top of the core (approximately
1 inch), as this possibly represents material
collected before penetration of the layer of
concern Place the remaining core into the
appropriate labeled sample container
Sample homogenization is not required
10 If volatile organic analysis is to be
performed, transfer the sample into an
appropriate, labeled sample container with a
stainless steel lab spoon, or equivalent and
secure the cap tightly Place the remainder
of the sample into a stamless steel, plastic, or
other appropriate homogenization container,
and mix thoroughly to obtain a homogenous
sample representative of the entire sampling
interval Then, either place the sample into
appropnate, labeled containers and secure the
3
-------
caps tightly, or, if composite samples are to
be collected, place a sample from another
sampling interval into the homogenization
container and mix thoroughly
When compositing is complete, place the
sample into appropnate, labeled containers
and secure the caps tightly
II If another sample is to be collected in the
same hole, but at a greater depth, reattach the
auger bit to the drill and assembly, and
follow steps 3 through II, making sure to
decontaminate the auger and tube sampler
between samples
12 Abandon the hole according to applicable
State regulations Generally, shallow holes
can simply be backfilled with the removed
soil material
7 2 3 Sampling at Depth with a Trier
The system consists of a trier, and a “Tn handle The
auger is driven into the soil to be sampled and used to
extract a core sample from the appropriate depth
The following procedure will be used to collect soil
samples with a sampling tner
Insert the trier (Figure 2. Appendix A) into
the material to be sampled at a 0° to 45° angle
from horizontal This orientation minimizes
the spillage of sample
2 Rotate the trier once or twice to cut a core of
material
3. Slowly withdraw the trier, making sure that
the slot is facing upward
4 If volatile organic analysis is to be
performed, transfer the sample into an
appropriate, labeled sample container with a
stainless steel lab spoon, or equivalent and
secure the cap tightly Place the remainder
of the sample into a stainless steel, plastic, or
other appropriate homogenization container,
and mix thoroughly to obtain a homogenous
sample representative of the entire sampling
interval Then, either place the sample into
appropriate, labeled containers and secure the
caps tightly, or, if composite samples are to
be collected, place a sample from another
sampling interval into the homogenization
container and mix thoroughly When
compositmg is complete, place the sample
into appropriate, labeled containers and
secure the caps tightly
7 2 4 Sampling at Depth with a Split
Spoon (Barrel) Sampler
The procedure for split spoon sampling describes the
collection and extraction of undisturbed soil cores of
18 or 24 inches in length A series of consecutive
cores may be extracted with a split spoon sampler to
give a complete soil column profile, or an auger may
be used to drill down to the desired depth for
sampling The split spoon is then driven to its
sampling depth through the bottom of the augured
hole and the core extracted
When split spoon sampling is performed to gain
geologic information, all work should be performed in
accordance with ASTM D 1586-67 (reapproved
1974)
The following procedures will be used for collecting
soil samples with a split spoon
Assemble the sampler by aligning both sides
of barrel and then screwing the drive shoe on
the bottom and the head piece on top
2 Place the sampler in a perpendicular position
on the sample material
3 Using a well nng, drive the tube Do not
drive past the bottom of the head piece or
compression of the sample will result
4. Record in the site logbook or on field data
sheets the length of the tube used to penetrate
the material being sampled, and the number
of blows required to obtain this depth
5 Withdraw the sampler, and open by
unscrewing the bit and head and splitting the
barrel The amount of recovery and soil type
should be recorded on the boring log If a
split sample is desired, a cleaned, stainless
steel knife should be used to divide the tube
contents in half, longitudinally This sampler
4
-------
is typically available in 2 and 3 1/2 inch
diameters However, in order to obtain the
required sample volume, use of a larger
barrel may be required
6 Without disturbing the core, transfer it to
appropriate labeled sample container(s) and
seal tightly
7 2 5 Test Pit/Trench Excavation
These relatively large excavations are used to remove
sections of soil, when detailed examination of soil
characteristics (horizontal, structure, color, etc) are
required It is the least cost effective sampling
method due to the relatively high cost of backhoe
operation
The following procedures will be used for collecting
soil samples from test pit/trench excavations
Prior to any excavation with a backhoe, it is
important to ensure that all sampling
locations are clear of utility lines, subsurface
pipes and poles (subsurface as well as above
surface)
2 Using the backhoe, a trench is dug to
approximately three feet in width and
approximately one foot below the cleared
sampling location Place excavated soils on
plastic sheets Trenches greater than five
feet deep must be sloped or protected by a
shoring system, as required by OSHA
regulations
3. A shovel is used to remove a one to two inch
layer of soil from the vertical face of the pit
where sampling is to be done
4 Samples are taken using a trowel, scoop, or
coring device at the desired intervals Be
sure to scrape the vertical face at the point of
sampling to remove any soil that may have
fallen from above, and to expose fresh soil
for sampling In many instances, samples
can be collected directly from the backhoe
bucket
5 If volatile organic analysis is to be
performed, transfer the sample into an
appropriate, labeled sample container with a
stainless steel lab spoon, or equivalent and
secure the cap tightly Place the remainder
of the sample mto a stainless steel, plastic, or
other appropriate homogenization container,
and mix thoroughly to obtain a homogenous
sample representative of the entire sampling
interval Then, either place the sample into
appropriate, labeled containers and secure the
caps tightly, or, if composite samples are to
be collected, place a sample from another
sampling interval into the homogenization
container and mix thoroughly When
compositing is complete, place the sample
into appropriate, labeled containers and
secure the caps tightly
6 Abandon the pit or excavation according to
applicable state regulations Generally,
shallow excavations can simply be backfil led
with the removed soil material
8.0 CALCULATIONS
This section is not applicable to this SOP
9.0 QUALITY ASSURANCE/
QUALITY CONTROL
There are no specific quality assurance (QA) activities
which apply to the implementation of these
procedures However, the following QA procedures
apply
All data must be documented on field data
sheets or within site logbooks
2 All instrumentation must be operated in
accordance with operating instructions as
supplied by the manufacturer, unless
otherwise specified in the work plan.
Equipment checkout and calibration
activities must occur prior to
sampling/operation, and they must be
documented
10.0 DATA VALIDATION
This section is not applicable to this SOP
11.0 HEALTH AND SAFETY
When working with potentially hazardous materials,
5
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follow U S EPA, OHSA and corporate health and de Vera, E R , B P Simmons, R D Stephen, and D L
safety procedures Storm Samplers and Sampling Procedures for
Hazardous Waste Streams 1980 EPA-600/2-80-0 18
12.0 REFERENCES
ASTM D 1586-67 (reapproved 1974), ASTM
Mason, B .1 , Preparation of Soil Sampling Protocol Committee on Standards, Philadelphia, PA
Technique and Strategies 1983 EPA-600/4-83.020
Barth, D S and B J Mason, Soil Sampling Quality
Assurance User’s Guide 1984 EPA-600/4-84.043
U S EPA Charactenzation of Hazardous Waste Sites
- A Methods Manual. Volume II Available
Sampling Methods, Second Edition 1984 EPA-
600/4-84-076
6
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APPENDIX A
Figures
FIGURE I Sampling Augers
TUBE
AUGER
BUCKET
AUGER
7
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APPENDIX A (Cont’d)
Figures
FIGURE 2 Sampling Tner
8
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SOIL GAS SAMPLING
SOP#• 2042
DATE: 06/01/96
REV.#.00
1.0 SCOPE AND APPLICATION
Soil gas monitoring provides a quick means of waste
site evaluation Using this method, underground
contamination can be identified, and the source,
extent, and movement of the pollutants can be traced
This standard operating procedure (SOP) outlines the
methods used by U.S EPA/ERT in installing soil gas
wells, measuring organic vapor levels in the soil gas
using a Photoionization Detector (PID), Flame
Ionization Detector (FID) and/or other air monitoring
devices, and sampling the soil gas using Tedlar bags,
Tena ( sorbent tubes, and/or Suinma canisters
These are standard (i e, typically applicable)
operating procedures which may be varied or changed
as required, dependent on site conditions, equipment
limitations or limitations imposed by the procedure
In all instances, the ultimate procedures employed
should be documented and associated with the final
report
Mention of trade names or commercial products does
not constitute U S EPA endorsement or
recommendation for use
2.0 METHOD SUMMARY
A 3f8 diameter hole is driven into the ground to a
depth of four to five feet using a commercially
available slam bar Soil gas can also be sampled at
other depths by the use of a longer bar or bar
attachments A l/4 0 D stauiless steel probe is
inserted into the hole The hole is then sealed around
the top of the probe using modeling clay The gas
contained in the interstitial spaces of the soil is
sampled by pulhng the sample through the probe
using an air sampling pump The sample may be
stored in Tedlar bags, drawn through sorbent
cartridges, or analyzed directly using a direct reading
instrument The air sampling pump is not used for
Summa canister sampling of soil gas Sampling is
achieved by soil gas equilibration with the evacuated
Summa canister
Other field air monitoring devices, such as the
combustible gas indicator (MSA CGIIO2 Meter,
Model 260) and the Organic Vapor Analyzer (Foxboro
OVA, Model 128), can also be used dependent on
specific site conditions Measurement of soil
temperature using a temperature probe may also be
desirable Bagged samples are usually analyzed in a
field laboratory using a portable Photovac GC
Power driven sampling probes may be utilized when
soil conditions make sampling by hand unfeasible
(i e, frozen ground, very dense clays, pavement, etc)
Commercially available soil gas sampling probes
(hollow, 1/2 = 0 D steel probes) can be driven to the
desired depth using a power hammer (e g, Bosch
Demolition Hammer or Geoprobe tm ) Samples can be
drawn through the probe itself, or through Teflon
tubing inserted through the probe and attached to the
probe point Samples are collected and analyzed as
described above
3.0 SAMPLE PRESERVATION,
CONTAINERS, HANDLING,
AND STORAGE
3.1 Tedlar Bags
Soil gas samples are generally contained in I 0-L
Tedlar bags Bagged samples are best stored in dark
plastic bags placed in coolers to protect the bags from
any damage that may occur in the field or in transit
In addition, coolers insure the integrity of the samples
by keeping them at a cool temperature and out of
direct sunlight Samples should be analyzed as soon
as possible, preferably within 24 - 48 hours
3.2 Tenax Tubes
Bagged samples can also be drawn onto Tenax or
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other sorbent tubes to undergo lab GCIMS analysis
If Tenax tubes are to be utilized, special care must be
taken to avoid contamination Handling of the tubes
should be kept to a minimum and only while weanng
nylon or other lint-free gloves, After sampling, each
tube should be stored in a clean, sealed culture tube,
the ends packed with clean glass wool to protect the
sorbent tube from breakage The culture tubes should
be kept cool and wrapped in aluminum foil to prevent
any photodegradation of samples (see Section 7 4)
3.3 Summa Canisters
The Summa canisters used for soil gas sampling have
a 6 liter sample capacity and are certified clean by
GCIMS analysis before being utilized in the field
Alter sampling is completed, they are stored and
shipped in travel cases
4.0 INTERFERENCES
POTENTIAL PROBLEMS
4.1 PID Measurements
AND
A number of factors can affect the response of a PID
(such as the HNu P1101) High humidity can cause
lamp fogging and decreased sensitivity This can be
significant when soil moisture levels are high, or
when a soil gas well is actually in groundwater High
concentrations of methane can cause a downscale
deflection of the meter High and low temperature,
electrical fields, FM radio transmission, and naturally
occumng compounds, such as terpenes in wooded
areas, will also affect instrument response
Other field screening instruments can be affected by
interferences Consult the manufacturers manuals
4.2 FED Measurements
A number of factors can affect the response of an FID
(such as the OVA model 128) High humidity can
cause the FD to flame out or not ignite at all This
can be significant when soil moisture levels are high,
or when a soil gas well is actually in groundwater
The FID can only read organic based compounds
(they must contain carbon in the molecular structure)
The FID also responds poorly to hydrocarbons and
halogenated hydrocarbons (such as gasoline, propane
fuel). High and low temperature, electrical fields and
FM radio transmission will also affect instrument
response
4.3 Factors Affecting Organic
Concentrations in Soil Gas
Concentrations in soil gas are affected by dissolution,
adsorption, and partitioning Partitioning refers to the
ratio of component found in a saturated vapor above
an aqueous solution to the amount in the solution, this
can, in theouy, be calculated using the Henry’s Law
constants Contaminants can also be adsorbed onto
inorganic soil components or “dissolved” in organic
components These factors can result in a lowering of
the partitioning coefficient
Soil “tightness” or amount of void space in the soil
matrix, will affect the rate of recharging of gas into
the soil gas well.
Existence of a high, or perched, water table, or of an
impermeable underlying layer (such as a clay lens or
layer of buried slag) may interfere with sampling of
the soil gas Knowledge of site geology is useful in
such situations, and can prevent inaccurate sampling
4.4 Soil Probe Clogging
A common problem with this sampling method is soil
probe clogging A clogged probe can be identified by
using an in-line vacuum gauge or by listening for the
soundofthepumplabormg Tins problem can usually
be eliminated by using a wire cable to clear probe (see
Section 7 1 3 )
4.5 Underground Utilities
Prior to selecting sample locations, an underground
utility search is recommended The local utility
companies can be contacted and requested to mark the
locations of their underground lines Sampling plans
can then be drawn up accordingly Each sample
location should also be screened with a metal detector
or magnetometer to verify that no underground pipes
or drums exist
5.0 EQUIPMENT/APPARATUS
5.1 Slam Bar Method
C Slam Bar (I per sampling team)
C Soil gas probes, stainless steel tubing, 1/4”
OD,5ftlength
C Flexible wire or cable used for clearing the
2
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tubing during insertion into the well
C “Quick Connect” fittings to connect sampling
probe tubing, monitoring instruments, and
Gilian pumps to appropriate fittings on
vacuum box
C Modeling clay
C Vacuum box for drawing a vacuum around
Tedlar bag for sample collection (I per
sampling team)
C Gilian pump Model HFSI l3A adjusted to
approximately 3 0 L/min (I to 2 per sample
team)
C 1/4” Teflon tubing, 2 ft to 3 ft lengths, for
replacement of contaminated sample line
C 1/4” Tygon tubing, to connect Teflon tubing
to probes and quick connect fittings
C Tedlar bags, 1 0 L, at least I bag per sample
point
C Soil Gas Sampling labels, field data sheets,
logbook, etc
C PID/FID, or other field air monitoring
devices, (I per sampling team)
C Ice chest, for carrying equipment and for
protection of samples (2 per sampling team)
C Metal detector or magnetometer, for
detecting underground utilities/pipes/drums
(I per sampling team).
C Photovac OC, for field-lab analysis of
bagged samples
C Summa canisters (plus their shipping cases)
for sample, storage and transportation
C Large dark plastic garbage bags
5.2 Power Hammer Method
C Bosch demolition hammer
C 1/2” 0 D steel probes, extensions, and
points.
C Dedicated aluminum sampling points
C Teflon tubing, 1/4”
C “Quick Connect” fittings to connect sampling
probe tubing, monitonng instruments, and
Gilian pumps to appropriate fittings on
vacuum box
C Modeling clay
C Vacuum box for drawing a vacuum around
Tedlar bag for sample collection (I per
sampling team).
C Gilian pump Model l-IFSII3A adjusted to
approximately 3 0 Lfmin (1 to 2 per sample
team)
C 1/4” Teflon tubing, 2 ft to 3 ft lengths, for
replacement of contaminated sample line
C 1/4” Tygon tubing, to connect Teflon tubing
to probes and quick connect fittings
C Tedlar bags, I 0 L, at least I bag per sample
point
C Soil Gas Sampling labels, field data sheets,
logbook, etc
C HNu Model P1101, or other field air
monitoring devices, (I per sampling team)
C Ice chest, for carrying equipment and for
protection of samples (2 per sampling team)
C Metal detector or magnetometer, for
detecting underground utilities/pipes/drums
(I per sampling team)
C Photovac GC, for field-lab analysis of
bagged samples
C Summa canisters (plus their shipping cases)
for sample, storage and transportation
C Generator w/extension cords
C High lift jack assembly for removing probes
5.3 Geoprobe TM Method
The Geoprobe is a hydraulically-operated sampling
device mounted in a customized four-wheel dnve
vehicle The sampling device can be deployed from
the truck and positioned over a sample location The
base of the sampling device is positioned on the
ground The weight of the vehicle is hydraulically
raised on the base As the weight of the vehicle is
transferred to the probe, the probe is pushed into the
ground A built-in hammer mechanism allows the
probe to be driven past some dense stratigraphic
horizons When the probe reaches the sample depth,
up to 50 feet under favorable geologic situations,
samples can be collected
Soil gas can be collected from specific depths in two
general ways One method involves withdrawing a
sample directly from the probe rods, after evacuating
a sufficient volume of air from the probe rods The
other method involves collecting a sample through
tubing attached by an adaptor to the bottom probe rod
section Correctly used, this method provides more
reliable results Manufacturer’s instructions and the
SOP for the Model 5400 Geoprobe TM Operation
should be followed when using this method
6.0 REAGENTS
C PIDIFID or calibration gases for field air
monitoring devices (such as methane and
3
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isobutylene)
C Deionized organic-free water, for
decontamination.
C Methanol, HPLC grade, for decontamination
C Ultra-zero grade compressed air, for field
blanks
C Standard gas preparations for Photovac GC
calibration and Tedlar bag spikes
C Propane Torch (for decontamination of steel
probes)
7.0 PROCEDURES
7.1 Soil Gas Well Installation
Initially a hole shghtly deeper than the
desued depth is made For sampling up to 5
feet, a 5-ft single piston slam bar is used
For deeper depths, a piston slam bar with
threaded 4-foot-long extensions can be used
Other techniques can be used, so long as
holes are of narrow diameter and no
contamination is introduced
2. After the hole is made, the slam bar is
carefully withdrawn to prevent collapse of
the walls of the hole The soil gas probe is
then inserted
3. It is necessary to prevent plugging of the
probe, especially for deeper holes A metal
wire or cable, slightly longer than the probe,
is placed in the probe prior to inserting into
the hole The probe is inserted to full depth,
then pulled up three to six inches, then
cleared by moving the cable up and down
The cable is removed before sampling
4 The top of the sample hole is sealed at the
surface against ambient air infiltration by
using modeling clay molded around the
probe at the surface of the hole
5 If conditions preclude hand installation of the
soil gas wells, the power driven system may
be employed The generator powered
demobtion hammer is used to drive the probe
to the desired depth (up to 12 Ft may be
attained with extensions) The probe is
pulled up 1-3 inches if the retractable point is
used No clay is needed to seal the hole
After sampling, the probe is retrieved using
the high lift jack assembly
6 If semi-permanent soil gas wells are
required, the dedicated aluminum probe
points are used These points are inserted
into the bottom of the power driven probe
and attached to the Teflon tubing The probe
is inserted as in step 5 When the probe is
removed, the point and Teflon tube remain in
the hole, which may be sealed by backfilling
with clean sand, soil, or bentonite
7.2 Screening with Field Instruments
The well volume ui be evacuated pnor to
sampling Connect the Gilian pump,
adjusted to 3 0 L/min, to the sample probe
using a section of Teflon tubing as a
connector The pump is turned on, and a
vacuum is pulled through the probe for
approximately 15 seconds Longer time is
required for sample wells of greater depths
2 After evacuation, the monitoring
instrument(s) (i e HNu or OVA) is
connected to the probe using a Teflon
connector When the reading is stable, or
peaks, the reading is recorded on soil gas
data sheets
3 Of course, readings may be above or below
the range set on the field instruments The
range may be reset, or the response recorded
as a greater than or less than figure
Recharge rate of the well with soil gas must
be considered when resampling at a different
range setting
7.3 Tedlar Bag Sampling
Follow step 7 2 I to evacuate well volume
If air monitoring instrument screening was
perforrnedpriorto sample taking, evacuation
is not necessary
2 Use the vacuum box and sampling train
(Figure I) to take the sample The sampling
train is designed to minimize the introduction
of contaminants and losses due to adsorption
All wetted parts are either Teflon or stainless
steel The vacuum is drawn indirectly to
avoid contamination from sample pumps
4
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3 The Tedlar bag is placed inside the vacuum
box, and attached to the sampling port The
sample probe is attached to the sampling port
via Teflon tubing and a “Quick Connect”
fitting
4 A vacuum is drawn around the outside of the
bag, using a Gilian pump connected to the
vacuum box evacuation port, via Tygon
tubing and a “Quick Connect” fitting The
vacuum causes the bag to inflate, drawing
the sample
5 Break the vacuum by removing the Tygon
line from the pump Remove the bagged
sample from the box and close valve
Record data on data sheets or in Iogbooks
Record the date, time, sample location ID,
and the PID/FID instrument reading(s) on
sample bag label
CAUTIOl I Labels should not be pasted directly onto
the bags, nor should bags be labeled directly using a
marker or pen Inks and adhesive may diffuse through
the bag material, contaminating the sample Place
labels on the edge of the bags, or tie the labels to the
metal eyelets provided on the bags. Markers with inks
containing volatile organics (i.e., permanent ink
markers) should not be used
Chain of Custody Sheets must accompany all samples
submitted to the field laboratory for analysis
7,4 Tena Tube Sampling
Samples collected in Tedlar bags may be adsorbed
onto Tenax tubes for further analysis by GCIMS
7.4 1 Additional Apparatus
A Syringe with a luer-lock tip capable of
drawing a soil gas or air sample from a
Tedlar bag onto a Tenax/CMS sorbent tube
The syringe capacity is dependent upon the
volume of sample begm drawn onto the
sorbent tube
B Adapters for fitting the sorbent tube between
the Tedlar bag and the sampling syringe
The adapter attaching the Tedlar bag to the
sorbent tube consists of a reducing union
(1/4” to 1/16” 0 D -- Swagelok cat
SS-400-6-ILV or equivalent) with a length of
1/4” 0 D Teflon tubing replacing the nut on
the 1/6’ (Tedlar bag) side A 1/4” I D
silicone 0-ring replaces the ferrules in the
nut on the 1/4” (sorbent tube) side of the
union
The adapter attaching the sampling syringe to
the sorbent tube consists of a reducing union
(1/4” to 1/16” OD -- Swagelok Cat #
SS-400-6-lLVorequivalent) with a 1/4” ID
silicone 0-nng replacing the ferrules in the
nut on the 1/4” (sorbent tube) side and the
needle of a luer-lock syringe needle inserted
into the 1116” side (Held in place with a
1/16” ferrule) The luer-lock end of the
needle can be attached to the sampling
syringe It is useful to have a luer-lock
on/off valve situated between the syringe and
the needle
C Two-stage glass sampling cartridge (1/4”
o D. x 1/8” I D x 5 118”) contained in a
flame-sealed tube (Manufacturer Supelco
Custom Tenax/Spherocarb Tubes) containing
two sorbent sections retained by glass wool
Front section 150 mg of Tenax-GC
Back section 150 mg of CMS (Carbonized
Molecular Sieve)
These tubes are prepared and cleaned in
accordance with EPA Method
EMSL/RTP-SOP-EMD-0l3 by the vendor.
The vendor sends ten tubes per lot made to
the REAC GCIMS Laboratory and they are
tested for cleanliness, precision, and
reproductability
D Teflon-capped culture tubes or stainless steel
tube containers for sorbent tube storage and
shipping These containers should be
conditioned by baking at 120 degrees C for at
least two hours The culture tubes should
contain a glass wool plug to prevent sorbent
tube breakage during transport
Reconditioning of the containers should
occur between uses or after extended periods
of disuse (i e two weeks or more)
E Nylon gloves or lint-free cloth (Hewlett
Packard Part # 8650-0030 or equivalent)
5
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7 4 2 Sample Collection
Handle sorbent tubes with care, using nylon gloves (or
other lint-free material) to avoid contamination
Immediately before sampling, break one end of the
sealed tube and remove the Tenax cartridge
Connect the valve on the Tedlar bag to the sorbent
tube adapter Connect the sorbent tube to the sorbent
tube adapter with the Tenax (white granular) side of
the tube facing the Tedlar bag Connect the sampling
syringe assembly to the CMS (black) side of the
sorbent tube. Fittings on the adapters should be
finer-tight Open the valve on the Tedlar bag Open
the on/off valve of the sampling synnge Depending
on work plan stipulations, at least 10% of the soil gas
samples analyzed by this GC method must be
submitted for confirmational GCIMS analysis
(according to modified methods TO-I [ Tenax
absorbent] and TO-2 [ Carbon Molecular Sieve (CMS)
absorbent)) Each soil gas sample must be absorbed on
replicate TenaxICMS tubes The volume absorbed on
a TenaxJCMS tube is dependent on the total
concentration of the compounds measured by the
photovac/GC or other applicable GC
Total Concentration ( m )
Sample Volume (mL )
7 4 4 Quality Assurance (QA)
Before field use, a QA check should be performed on
each batch of sorbent tubes by analyzing a tube by
thermal desorptionlciyogenic trapping GC/lvlS
At least one blank sample must be submitted with
each set of samples collected at a site This trip blank
must be treated the same as the sample tubes except
no sample will be drawn through the tube
Sample tubes should be stored out of UV light (i e,
sunlight) and kept on ice until analysis Samples
should be taken in duplicate, when possible
7.5 Summa Canister Sampling
Follow step 7 2 1 to evacuate well volume
If PID/FID readings were taken prior to
taking a sample, evacuation is not necessary
2 Attach a certified clean, evacuated 6-liter
Summa canister via the 1/4” Teflon tubing
3 Open valve on Summa canister The soil gas
sample is drawn into the canister by pressure
equilibration The approximate sampling
time for a 6 liter canister is 20 minutes
Use Senal Dilution
10 - 50
20-100
100-250
>10
10
5
After sampling, remove the tube from the sampling
train with gloves or a clean cloth DO NOT LABEL
OR WRITE ON THE TENAX/CMS TUBE
Place the sorbent tube in a conditioned stainless steel
tube holder or culture tube, Culture tube caps should
be sealed with Teflon tape.
7 4.3 Sample Labeling
Each sample tube container (not tube) must be labeled
with the site name, sample station number, date
sampled, and volume sampled
Chain of custody sheets must accompany all samples
to the laboratory
4 Site name, sample location, number, and date
must be recorded on a chain of custody form
and on a blank tag attached to the canister
8.0 CALCULATIONS
8.1 Field Screening Instruments
Instrument readings are usually read directly from the
meter In some cases, the background level at the soil
gas station may be subtracted
Final Reading = Sample Reading - Background
8.2 Photovac GC Analysis
Calculations used to determine concentrations of
individual components by Photovac GC analysis are
beyond the scope of this SOP and are covered in ERT
SOP #2109, Pliozovac GC Analysis for Soil Water
andAir/Soil Gas
6
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9.0 CALIBRATION
9.1 Field Instruments
It is recommended that the manufacturers’ manuals be
consulted for correct use and calibration of all
instrumentation
9.2 Gilian Model HFS1I3A Air
Sam pling Pumps
Flow should be set at approximately 3 0 L/min,
accurate flow adjustment is not necessary Pumps
should be calibrated pnor to bringing into the field
10.0 QUALITY ASSURANCE/
QUALITY CONTROL
10.1 Sample Probe Contamination
Sample probe contamination is checked between each
sample by drawing ambient air through the probe via
a Gilian pump and checking the response of the
FIDIPID If readings are higher than background,
replacement or decontamination is necessary
Sample probes may be decontaminated simply by
drawing ambient air through the probe until the HNu
reading is at background More persistent
contamination can be washed out using methanol and
water, then air drying For persistent volatile
contammation, use of a portable propane torch may be
needed Using a pair of pliers to hold the probe, run
the torch up and down the length of the sample probe
for approximately 1-2 minutes Let the probe cool
before handling When using this method, make sure
to wear gloves to prevent burns Having more than
one probe per sample team will reduce lag times
between sample stations while probes are
decontaminated.
10.2 Sample Train Contamination
The Teflon line forming the sample train from the
probe to the Tedlar bag should be changed on a daily
basis If visible contamination (soil or water) is
drawn into the sampling train, it should be changed
unmediately When sampling in highly contaminated
areas, the sampling tram should be purged with
ambient air, via a Gilian pump, for approximately 30
seconds between each sample After purging, the
sampling train can be checked using an FID or PID, or
other field monitoring device, to establish the
cleanliness of the Teflon line
10.3 FIDIPID Calibration
The FID and PIDs should be calibrated at least once
a day using the appropriate calibration gases
10.4 Field Blanks
Each cooler contaming samples should also contain
one Tedlar bag of ultra-zero grade air, acting as a field
blank The field blank should accompany the samples
in the field (while being collected) and when they are
delivered for analysis A fresh blank must be
provided to be placed in the empty cooler pending
additional sample collection One new field blank per
cooler of samples is required A chain of custody
sheet must accompany each cooler of samples and
should include the blank that is dedicated to that group
of samples
10.5 Trip Standards
Each cooler containing samples should contain a
Tedlar bag of standard gas to calibrate the analytical
instruments (Photovac GC, etc) This trip standard
will be used to determine any changes in
concentrations of the target compounds during the
course of the sampling day (e g , migration through
the sample bag, degradation, or adsorption) A fresh
trip standard must be provided and placed in each
cooler pending additional sample collection A chain
of custody sheet should accompany each cooler of
samples and should include the trip standard that is
dedicated to that group of samples
10.6 Tedlar Bag Check
Pnor to use, one bag should be removed from each lot
(case of 100) of Tedlar bags to be used for sampling
and checked for possible contamination as follows
the test bag should be filled with ultra-zero grade air,
a sample should be drawn from the bag and analyzed
via Photovac GC or whatever method is to be used for
sample analysis This procedure will ensure sample
container cleanliness prior to the start of the sampling
effort
7
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10.7 Sum ma Canister Check
From each lot of four cleaned Summa canisters, one
is to be removed for a GC/MS certification check If
the canister passes certification, then it is re-evacuated
and all four canisters from that lot are available for
sampling
lithe chosen canister is contaminated, then the entire
lot of four Summas must be recleaned, and a single
canister is re-analyzed by GCIMS for certification
10.8 Options
10.8.1 Duplicate Samples
A minimum of 5% of all samples should be collected
in duplicate (i e, if a total of 100 samples are to be
collected, five samples should be duplicated) In
choosing which samples to duplicate, the following
cnteria applies if, after filling the first Tedlar bag,
and, evacuating the well for 15 seconds, the second
HN (or other field monitoring device being used)
reading matches or is close to (within 50%) the first
reading, a duplicate sample may be taken
10.8.2 Spikes
A Tedlar bag spike and Tenax tube spike may be
desirable in situations where high concentrations of
contaminants other than the target compounds are
found to exist (landfills, etc) The additional level of
QA/QC attamed by this practice can be useful in
determining the effects of interferences caused by
these non-target compounds Summa canisters
containing samples are not spiked.
11.0 DATA VALIDATION
11.1 Blanks (Field and Tedlar Bag
Check)
For each target compound, the level of concentration
found in the sample must be greater than three times
the level (for that compound) found in the field blank
which accompanied that sample to be considered
valid The same cntena apply to target compounds
detected in the Tedlar bag pm-sampling contamination
check
12.0 HEALTH AND
CONSIDERATIONS
SAFETY
Due to the remote nature of sampling soil gas, special
considerations can be taken with regard to health and
safety Because the sample is being drawn from
underground, and no contamination is introduced into
the breathing zone, soil gas sampling usually occurs in
Level D Ambient air is constantly monitored using
the HNu P1101 to obtain background readings during
the sampling procedure As long as the levels in
ambient air do not rise above background, no upgrade
of the level of protection is needed
When conducting soil gas sampling, leather gloves
should be worn, and proper slam bar techniques
should be implemented (bend knees) Also, an
underground utility search should be performed prior
to sampling (See Section 4 5)
13.0 REFERENCES
Gilian Instrument Corp, instruction Manual for Hi
Flow Sampler HFSI 13, HFS 113 T, HFS I l3U,
HFS 113 UT, 1983
HNu Systems, Inc , Instruction Manual for Model P1
101 Photoionization Analyzer, 1975
N J D E P. Field Sampling Procedures Manual,
Hazardous Waste Programs, February, 1988
Roy F Weston, mc, Weston Instrumentation Manual,
Volume I, 1987
U S E P A, Characterization of Hazardous Waste
Sites - A Methods Manual Volume II, Available
Sampling Methods, 2nd Edition, EPA-600/4-84-076,
December, 1984
8
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APPENDIX A
Figure
FIGURE 1 Sampling Train Schematic
VACUAT1ON
VACUUM PORT
i/( TEFLON TUBING
SCREENING
PORT
MODELING
CLAY
QUICK CONNECt•
FITTING
1/4
SAMPLE
SAMPLE
WEll
9
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APPENDIX B
HNu Field Protocol
Field Procedure
The following sections detail the procedures that are to be followed when using the HNu in the field
Startup Procedure
a Before attaching the probe, check the function switch on the control panel to ensure that it is in the
off position. Attach the probe by plugging it into the interface on the top of the readout module
Use care in aligning the prongs in the probe cord with the plug in, don’t force
b Turn the function switch to the battery check position The needle on the meter should read within
or above the green battery are on the scale If not, recharge the battery If the red indicator light
comes on, the battery needs recharging
c Turn the function switch to any range setting Look into the end of the probe for no more than two
to three seconds to see if the lamp is on If it is on, it will give a purple glow Do not stare into the
probe any longer than three seconds Long term exposure to UV light can damage eyes Also,
listen for the hum of the fan motor
d To ZERO the instrument, turn the function switch to the standby position and rotate the zero
adjustment until the meter reads zero A calibration gas is not needed since this is an electronic
zero adjustment. If the span adjustment setting is changed after the zero is set, the zero should be
rechecked and adjusted, if necessary Wait 15 to 20 seconds to ensure that the zero reading is
stable If necessary, readjust the zero
Operational Check
a Follow the startup procedure
b With the instrument set on the 0-20 range, hold a solvent-based major market near the probe tip
If the meter deflects upscale, the instrument is working
Field Calibration Procedure
a Follow the startup procedure and the operational check
b Set the function switch to the range setting for the concentration of the calibration gas
c Attach a regulator (HNu 101-351) to a disposable cylinder of isobutylene gas (l-INu 101-351)
Connect the regulator to the probe of the HNu with a piece of clean Tygon tubing Turn on the
value on the regulator
d After fifteen seconds, adjust the span dial until the meter reading equals the concentration of the
calibration gas used Be careful to unlock the span dial before adjusting it If the span has to be
set below 3 0, calibration internally or return to equipment maintenance for repair
10
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e Record in the field logbook the instrument ID no (EPA decal or serial number if the instrument
is a rental), the initial and final span settings, the date and time, concentration and type of
calibration has used, and the name of the person who calibrated the instrument
Operation
a Follow the startup procedure, operational check, and calibration check
b. Set the function switch to the appropriate range If the concentration of gases or vapors is unknown,
set the function switch to the 0-20 ppm range Adjust it if necessary
c. While taking care not to permit the HNu to be exposed to excessive moisture, dirt, or
contamination, monitor the work activity as specified in the Site Health and Safety Plan
d When the activity is completed or at the end of the day, carefully clean the outside of the HNu with
a damp di osable towel to remove any visible dirt Return the HNu to a secure area and place on
charge
e With the exception of the probe’s inlet and exhaust, the HNu can be wrapped in clear plastic to
prevent it form becoming contaminated and to prevent water from getting inside in the event of
- precipitation.
I I
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MODEL 5400
GEOPROBETM OPERATION
SOP#: 2050
DATE: 03/27/96
REV #.00
1.0 SCOPE AND APPLICATION
The purpose of this standard operating procedure
(SOP) is to descnbe the collection of representative
soil, soil-gas, and groundwater samples using a Model
5400 Geoprobe sampling device Any deviations
from these procedures should be documented in the
site/field logbook and stated in project deliverables
Mention of trade names or commercial products does
not constitute U S Environmental Protection Agency
(U S EPA) endorsement or recommendation for use
2.0 METHOD SUMMARY
The Geoprobe sampling device is used to collect
soil, soil-gas and groundwater samples at specific
depths below ground surface (B OS) The Geopmbe
is hydraulically powered and is mount d in a
customized four-wheel drive vehicle The base of the
sampling device is positioned on the ground over the
sampling location and the vehicle is hydraulically
raised on the base As the weight of the vehicle is
transferred to the probe, the probe is pushed into the
ground A built-in hammer mechanism allows the
probe to be driven through dense materials
Maximum depth penetration under favorable
circumstances is about 50 feet Components of the
Model 5400 Geoprob& are shown in Figures 1
through 6 (Appendix A)
Soil samples are collected with a specially-designed
sample tube The sample tube is pushed and/or
vibrated to a specified depth (approximately one foot
above the intended sample interval) The interior plug
of the sample tube is removed by inserting small-
diameter threaded rods The sample tube is then
driven an additional foot to collect the samples. The
probe sections and sample tube are then withdrawn
and the sample is extruded from the tube into sample
jars
Soil gas can be collected in two ways One method
involves withdrawing a sample directly from the
probe rods, after evacuating a sufficient volume of air
from the probe rods The other method involves
collecting a sample through tubing attached by an
adaptor to the bottom probe section Correctly used,
the latter method provides more reliable results
Slotted lengths of probe can be used to collect
groundwater samples if the probe rods can be driven
to the water table Groundwater samples are collected
using either a penstaltic pump or a small bailer
3.0 SAMPLE PRESERVATION
CONTAINERS, HANDLING AND
STORAGE
Refer to specific ERT SOPs for procedures
appropriate to the matrix, parameters and sampling
objector
Applicable ERT SOPs include.
ERT #20 12, Soil Sampling
ERT #2007, Groundwater Well Sampling
ERT #2042, Soil Gas Sampling
4.0 INTERFERENCES
POTENTIAL PROBLEMS
AND
A preliminary site survey should identify areas to be
avoided with the truck All underground utilities
should be located and avoided during sampling
Begin sampling activities with an adequate fuel
supply
Decontamination of sampling tubes, probe rods,
adaptors, non-expendable points and other equipment
that contacts the soil is necessary to prevent cross-
contamination of samples Dunng sampling, the
bottom portion and outside of the sampling tubes can
be contaminated with soil from other depth intervals
-------
Care must be taken to prevent soil which does not
represent the sampled interval form being
incorporated into the sample Excess soil should be
carefully wiped from the outside surface of the
sampling tube and the bottom 3 inches of the sample
should be discarded before extruding the sample into
a sample jar
The amount of sample to be collected and the proper
sample container type (i e., glass, plastic), chemical
preservation, and storage requirements are dependent
upon the parameter(s) of interest Guidelines for the
containment, preservation, handling and storage of
soil-gas samples are described in ERT SOP #2042,
Soil-Gas Sampling
Obtaining sufficient volume of soil for multiple
analyses from one sample location may present a
problem. The Geopmbe soil sampling system
recovers a limited volume of soil and it is not possible
to reenter the same hole and collect additional soil
When multiple analyses are to be performed on soil
samples collected with the Geoprobe , it is important
that the relative importance of the analyses be
identified. Identifying the order of importance will
ensure that the limited sample volume will be used for
the most crucial analyses.
5.0 EQUIPMENT/APPARATUS
Sampling with the Geopmbe involves use of the
equipment listed below Some of the equipment is
used for all sample types, others are specific to soil
(S), soil gas (SG), or groundwater (GW) as noted
C Geoprobe” sampling device
C Threaded probe rods (36”, 24”, and 12”
lengths)
C Drive Caps
C Pull Caps
C Rod Extractor
C Expendable Point Holders
C Expendable Dnve Points
C Solid Drive Points
C Extension Rods
C Extension Rod Couplers
C Extension Rod Handle
C Hammer Anvil
C Hammer Latch
C Hammer Latch Tool
C Drill Steels
C Carbide-Tipped Drill Bit
C Mill-Slotted Well Point (OW)
C Threaded Drive Point (OW)
C Well Mini-Bailer (GW)
C Tubing Bottom Check Valve (OW)
C 3/8” 0 D Low Density Polyethylene Tubing
(OW, SO)
C Gas Sampling Adaptor and Cap (SG)
C Teflon Tape
C Neoprene “0” - Rings (SO)
C Vacuum System (mounted in vehicle) (SO)
C Piston Tip (S)
C Piston Rod (S)
C Piston Stop (S)
C Sample Tube (Il 5” in length) (S)
C Vinyl Ends Caps (S)
C Sample Extruder (S)
C Extruder Pistons (Wooden Dowels) (S)
C Wire Brush
C Brush Adapters
C Cleaning Brush (Bottle)
6.0 REAGENTS
Decontamination solutions are specified in ERT
SOP #2006, Sampling Equipment Decontamination
7.0 PROCEDURES
Portions of the following sections have been
condensed from the Model 5400 Geoprobe
Operations Manual(l) Refer to this manual for more
detailed information concerning equipment
specifications, general maintenance, tools, throttle
control, clutch pump, GSK-58 Hammer, and trouble-
shooting A copy of this manual will be maintained
with the Geoprobe TM and on file in the Quality
Assurance (QA) office
7.1 Preparation
Determine extent of the sampling effort,
sample matrices to be collected, and types
and amounts of equipment and supplies
required to complete the sampling effort
2 Obtain and organize necessary sampling and
monitoring equipment
3 Decontaminate or pre-clean equipment, and
ensure that it is in working order
4 Perform a general site survey prior to site
2
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entry in accordance with the site-specific
Health and Safety Plan
5. Use stakes or flagging to identifS and mark
all sampling locations All sample locations
should be cleared for utilities prior to
sampling.
7.2 Setup of Geoprobe
I Back carrier vehicle to probing location
2 Shift the vehicle to park and shut off ignition
3 Set parking brake and place chocks under
rear tires
4 Attach exhaust hoses so exhaust blows
downwind of the sampling location (this is
particularly important during soil gas
sampling)
5 Start engine using the remote ignition at the
Geoprobe” operator position
6 Activate hydrauhc system by turning on the
Electrical Control Switch located on the
Geoprobe tm ’ electrical control panel (Figure
I, Appendix A) When positioning the
probe, always use the SLOW speed The
SLOW speed switch is located on the
hydraulic control panel (Figure 2, Appendix
A)
Important: Check for clearance on
vehicle real before folding Geoprobe 1M out
of the carrier vehicle.
7 Laterally extend the Geoprobe tm ’ from the
vehicle as far as possible by pulling the
EXTEND control lever toward the back of
the vehicle while the Geoprobe ’ ”‘ is
horizontal
8 Using the FOOT control, lower the Demck
Slide so it is below cylinder (A) before
folding the Geoprobe”‘ out of the camer
vehicle (Figure 3, Appendix A) This will
ensure clearance at the roof of the vehicle
9 Use the FOLD, FOOT, and EXTEND
controls to place Geopmbe ’ to the exact
probing location Never begin probing in the
fully extended position
10 Using the FOLD control, adjust the long axis
of the probe cylinder so that it is
perpendicular (visually) to the ground
surface
II Using the FOOT control, put the weight of
the vehicle on the probe unit Do not raise
the rear of the vehicle more than six inches
Important: Keep rear vehicle wheels on
the ground surface when transferring the
weight of the vehicle to the probe unit.
Otherwise, vehicle may shift when
probing begins.
12. When the probe axis is vertical and the
weight of the vehicle is on the probe unit,
probing is ready to begin
7.3 Drilling Through
Pavement or Concrete
Surface
Position camer vehicle to drilling location
2 Fold unit out of camer vehicle
3 Deactivate hydraulics
4 Insert carbide-tipped drill bit into hammer
5 Activate HAMMER ROTATION control by
turning knob counter-clockwise (Figure 4,
Appendix A) This allows the drill bit to
rotate when the HAMMER control is
pressed
6 Press down on HAMMER control to activate
counterclockwise rotation
7 Both the HAMMER control and the PROBE
control must be used when drilling through
the surface (Figure 4, Appendix A) Fully
depress the HAMMER control, and
incrementally lower the bit gradually into the
pavement by periodically depressing the
PROBE control
8 When the surface has been penetrated, turn
the HAMMER Control Valve knob
3
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clockwise to deactivate hammer rotation and
remove the drill bit from the HA vllv1ER
Important: Be sure to deactivate the
rotary action before driving probe rods.
7.4 Probing
Position the carrier vehicle to the desired
sampling location and set the vehicle parking
brake
2 Deploy Geoprobe” ’ Sampling Device
3 Make sure the hydrauhc system is turned off
4 Lift up latch and insert hammer anvil into
hammer - push latch back in (Figure 5,
Appendix A).
5 Thread the dnve cap onto the male end of the
probe rod
6. Thread an expendable point holder onto the
other end of the first probe rod
7 Slip an expendable drive point into point
holder,
8 Position the leading probe rod with
expendable drive point in the center of the
derrick foot and directly below the hammer
anvil.
Important: Positioning the first probe rod
is critical in order to drive the probe rod
vertically. Therefore, both the probe rod
and the probe cylinder shaft must be in
the vertical position (Figure 6, Appendh
A).
9 To begin probing, activate the hydraulics and
push the PROBE Control downward When
advancing the first probe rod, always use the
SLOW speed Many times the probe rods
can be advanced using only the weight of the
camer vehicle When this is the case, only
the PROBE control is used
Important: When advancing rods, always
keep the probe rods parallel to the probe
cylinder shaft (Figure 6, Appendix A)
This is done by making minor
adjustments with the FOLD controL
Failure to keep probe rods parallel to
probe cylinder shaft may result In broken
rods and Increased difficulty In achieving
desired sampling depth.
7.5 Probing - Percussion Hammer
The percussion hammer must be used in situations
where the weight of the vehicle is not sufficient to
advance the probe rods
Make sure the Hammer Rotation Valve is
closed
2 Using the PROBE control to advance the rod,
press down the HAMMER control to allow
percussion to drive the rods (Figure 2,
Appendix A)
Important: Always keep static weight on
the probe rod or the rod will vibrate and
chatter while you are hammering, causing
rod threads to fracture and break.
3 Keep the hammer tight to the drive cap so the
rod will not vibrate
4 Periodically stop hammenng and check if the
probe rods can be advanced by pushing only
5 Any time the downward progress of the
probe rods is refused, the demck foot may
lift off of the ground surface When this
happens, reduce pressure on the PROBE
control. Do not allow the foot to rise more
than six inches off the ground or the vehicle’s
wheels may lift off the ground surface,
causing the vehicle to shift (Figure 6,
Appendix A)
6 As the derrick foot is raised off the ground
surface, the probe cylinder may not be in a
perpendicular position If this happens, use
the FOLD control to correct the probe
cylinder position
7.6 Probing - Adding Rods
Standard probe rods are three feet in length
If the desired depth is more than three feet,
4
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another rod must be threaded onto the rod
that has been driven into the ground In
order to ensure a vacuum-tight seal (soil-gas
sampling), two wraps of teflon tape around
the thread is recommended
2. Using the PROBE control, raise the probe
cylinder as high as possible
Important: Always deactivate hydraulics
when adding rods.
3 Deactivate hydraulics
4 Unthread the drive cap from the probe rod
that is in the ground
5 Wrap teflon tape around the threads
6. Thread the drive cap onto the male end of the
next probe rod to be used
7. After threading the drive cap onto the rod to
be added, thread the rod onto the probe rod
that has been driven into the ground Make
sure threads have been teflon taped.
Continue probing
8 Continue these steps until the desired
sampling depth has been reached
7.7 Probing/Pulling Rods
I Once the probe rods have been driven to
depth, they can also be pulled using the
Geoprobe Machine
2 Turn off the hydraulics
3 Lift up latch and take the hammer anvil out
of the hammer.
4. Replace the drive cap from the last probe rod
driven with a pull cap
5 Lift up the hammer latch.
6 Activate the hydraulics.
7 Hold down on the PROBE control, and move
the probe cylinder down until the latch can
be closed over the pull cap
Important: If the latch will not close over
the pull cap, adjust the derrick assembly
by using the extend control. This wil
allow you to center the pull cap directly
below the hammer latch.
8 Retract the probe rods by pulling up on the
PROBE control
Important: Do not raise the probe
cylinder all the way when pulling probe
rods or It will be impossible to detach a
rod that has been pulled out. However, It
is necessary to raise the probe cylinder far
enough to allow the next probe section to
be pulled.
9 After retracting the first probe rod, lower the
probe cylinder only slightly to ease the
pressure off of the hammer latch
10 Attach a clamping device to the base of the
rods where it meets the ground to prevent
rods from falling back into the hole
II Raise the hammer latch
12 Hold the PROBE control up and raise the
probe cylinder as high as possible
13. Unthread the pull cap from the retracted rod
14 Unthread the retracted rod
IS Thread the pull cap onto the next rod that is
to be pulled
16 Continue these steps until all the rods are
retracted from the hole
17 Decontaminate all portions of the equipment
that have been in contact with the soil, soil
gas and groundwater
7,8 Soil-Gas Sampling
Interior Tubing
Without
Follow procedures outlined in Sections 7 1
through 7 6
2 Remove hammer anvil from hammer
5
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3 Thread on pull cap to end of probe rod
4 Retract rod approximately SIX inches
Retraction of the rod disengages expendable
drive point and allows for soil vapor to enter
rod
5 Unthread pull cap and replace it with a gas
sampling cap Cap is furnished with barbed
hose connector
Important: Shut engine off before taking
sample (eihaust fumes can cause faulty
sample data).
6 Turn vacuum pump on and allow vacuum to
build in tank
7 Open line control valve For each rod used,
purge 300 liters of volume Example Three
rods used = 900 liters = .900 on gauge
8 After achieving sufficient purge volume,
close valve and allow sample line pressure
gauge to return to zero This returns sample
train to atmospheric pressure
9 The vapor sample can now be taken
I. Pinch hose near gas sampling cap to
prevent any outside vapors from
entering the rods
2 Insert syringe needle into center of
barbed hose connector and
withdraw vapor sample
10 To maintain suction at the sampling location,
periodically drain the vacuum tank
11 To remove rods, follow procedures outlined
in Section 7.7
7.9 Soil-Gas Sampling With Post-Run
Tubing (PRT)
1. Follow procedures outlined in Sections 7 1
through 7 6
2 Retract rod approximately six inches
Retraction of rod disengages expendable
drive point and allows for soil vapor to enter
rod
3 Remove pull cap from the end of the probe
rod
4 Position the Geoprobe TM to allow room to
work.
5 Secure FRI Tubing Adapter with “0” - Ring
to selected tubing
6 Insert the adapter end of the tubing down the
inside diameter of the probe rods
7 Feed the tubing down the hole until it hits
bottom on the expendable point holder Cut
the tubing approximately two feet from the
top probe rod
8 Grasp excess tubing and apply some
downward pressure while turning it in a
counter-clockwise motion to engage the
adapter threads with the expendable point
holder
9 Pull up lightly on the tubing to test
engagement of threads
10 Connect the outer end of the tubing to silicon
tubing and vacuum hose (or other sampling
apparatus)
11 Follow the appropriate sampling procedure
(ERT SOP #2042, Soil Gas Sampling) to
collect a soil-gas sample
12 After collecting a sample, disconnect the
tubing from the vacuum hose or sampling
system
13. Pull up firmly on the tubing until it releases
from the adapter at the bottom of the hole
14 Extract the probe rods from the ground and
recover the expendable point holder with the
attached adapter
6
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15 Inspect the nO”-ring at the base of the
adapter to verify that proper sealing was
achieved during sampling, The O”-nng
should be compressed.
Note: If the “O”-ring is not compressed,
vapors from within the probe sections may
have been collected rather than vapors
from the intended sample interval.
7.10 Soil Sampling
I Follow procedures outlined in Sections 7 1
through 7 6
2 Assemble soil-sampling tube
J
I Thread piston rod into piston tip
2 Insert piston tip into sample tube,
seating piston tip into cutting edge
of sample tube.
3 Thread drive head into threaded end
of sample tube.
4. Thread piston stop pin into drive
head Stop pin should be tightened
with wrench so that ij exerts
pressure against the piston rod
3 Attach assembled sampler onto leading probe
rod
4 Drive the sampler with the attached probe
rods to the top of the mterval to be sampled
5. Move probe unit back from the top of the
probe rods to allow work room
6 Remove drive cap and lower extension rods
into inside diameter of probe rods using
couplers to jom rods together
7 Attach extension rod handle to top extension
rod.
8. Rotate extension rod handle clockwise until
the leading extension rod is threaded into the
piston stop in downhole
9. Continue to rotate extension rod handle
clockwise until reverse-threaded stop-pin has
disengaged from the drive head
10 Remove extension rods and attached stop-pin
from the probe rods
II Replace drive cap onto top probe rod
12 Mark the top probe rod with a marker or tape
at the appropriate distance above the ground
surface (dependent on sample tube length).
13 Drive probe rods and sampler the designated
distance Be careful not to overdrive the
sampler which could compact the soil sample
in the tube, making it difficult to extrude
Important: Documentation of samp
location should include both surface ami
subsurface Idenl fiers. Example: Correct
Method - Sample Location S-6, 12.0’ -
13.0’. Incorrect Method - Samp
Location S-6, 12.0’.
14 Retract probe rods from the hole and recover
the sample tube Inspect the sample tube to
confirm that a sample was recovered
15 Disassemble sampler Remove all parts
16 Position extruder rack on the foot of the
Geoprobe’ demck
17 Insert sample tube into extruder rack with the
cutting end up
18 Insert hammer anvil into hammer
19 Position the extruder piston (wood dowel)
and push sample out of the tube using the
PROBE control on the Geoprobe TM Collect
the sample as it is extruded in an appropriate
sample container.
Caution: use care when performing thh
task. Apply downward pressure
gradually. Use of excessive force couki
result in injury to operator or damage t
tools. Make sure proper diameter
extruder piston is used.
20 To remove rods follow procedures outlined
in Section 7 7
7
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7.11 Groundwater Sampling
Follow Sections 7 1 thorough 7 6 with the
following exception the Mill-Slotted Well
Rod with attached threaded drive point
should be the first section probed into the
ground Multiple sections of mill-slotted
well rods can be used to provide a greater
vertical section into which groundwater can
flow.
2 Probe to a depth at which groundwater is
expected
3 Remove Dnve Cap and insert an electric
water-level indicator to determine if water
has entered the slotted sections of probe rod
Refer to ERT SOP #2043, Water Level
Measurement, to determine water level
4 If water is not detected in the probe rods,
replace the dnve cap and continue probing.
Stop after each additional probe length and
determine if groundwater has entered the
slotted rods
5 After the probe rods have been dnven into
the saturated zone, sufficient time should be
allowed for the water level in the probe rods
to stabilize
Note: It will be difficult If not impossible
to collect a groundwa r sample in aquifer
material small enough to pass through the
slots (<0.02 Inch diameter).
6 Groundwater samples may be collected with
the 20-mL well Mini-Bailer or a pumping
device If samples are being collected for
volatile organic analysis (VOA), the 20-mL
Well Mini-Bailer should be used If samples
are being collected for a variety of analyses,
VOA samples should be collected first using
the bailer Remaining samples can be
collected by pumping water to the surface
Withdrawing water with the pump is more
efficient than collecting water with the 20-
mL well Mini-Bailer.
Important: Documentation of sample
location should Include both surface and
subsurface identifiers. Example: Sample
Location GW-6, 17’-21’ bgs, water level in
probe rods is 17 feet bgs, and the leading
section of probe rod is 21 feet bgs. TIn
water sample is from this zone, not from
17 feet bgs or 21 feet bgs.
7 Remove rods following procedures outlined
in Section 7 7
8.0 CALCULATIONS
Calculating Vapor Purge Volume for Soil-Gas
Sampling without Interior Tubing
Volume of Air to be Purged (Liters) = 300 x
Number of Rods in the Ground
Volume in Liters/1000 = Reading
Vacuum Pump Instrument Gauge
9.0 QUALITY ASSURANCE!
QUALITY CONTROL
The following general QA procedures apply
All data must be documented on field data
sheets or within site logbooks
2 All instrumentation must be operated in
accordance with operating instructions as
supplied by the manufacturer, unless
otherwise specified in the work plan
Equipment checkout and calibration
activities must occur prior to
sampling/operation and they must be
documented
10.0 DATA VALIDATION
This section is not applicable to this SOP
11.0 HEALTH AND SAFETY
When working with potentially hazardous materials,
follow U S EPA, OSHA and the REAC site specific
Health and Safety Plan The following is a list of
health and safety precautions which specifically apply
to Geoprobe tm operation
Always put vehicle in ‘park”, set emergency
the brake, and place chocks under the tires,
before engaging remote ignition
on
8
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2 If vehicle is parked onaloose or soft surface, 13 Always remove the hammer anvil or other
do not fully raise rear of vehicle with probe tool from the machine before folding the
foot, as vehicle may fall or move machine to the horizontal position
3 Always extend the probe unit out from the 14 The vehicle catalytic converter is hot and
vehicle and deploy the foot to clear vehicle may present a fire hazard when operating
roof lane before folding the probe unit out over dry grass or combustibles
4 Operators should wear OSHA approved 15 Geoprobe TM operators must wear ear
steel-toed shoes and keep feet clear of probe protection OSHA approved ear protection
foot for sound levels exceeding 85 dba is
recommended
5 Operator should wear ANSI approved hard
hats 16 Locations of buried or underground utilities
and services must be known before starting
6. Only one person should operate the probe to drill or probe
machine and the assemble or disassemble
probe rods and accessories 17 Shutdown the hydraulic system and stop the
vehicle engine before attempting to clean or
7 Neverplace hands on top of a rod while it is service the equipment
under the machine
18 Exercise extreme caution when using
8 Turn off the hydraulic system while changing extnider pistons (wooden dowels) to extrude
rods, inserting the hammer anvil, or attaching soil from sample tubes Soil in the sample
accessories tube may be compacted to the point that the
extnider piston will break or shatter before it
9. Operator must stand on the control side of will push the sample out
the probe machine, clear of the probe foot
and mast, while operating controls 19 A dry chemical fire extinguisher (Type ABC)
should be kept with the vehicle at fl times
10 Wear safety glasses at all times during the
operation of this machine 12.0 REFERENCES
11 Never continue to exert downward pressure 1 Model 5400 Geoprob&” Operations Manual
on the probe rods when the probe foot has Geoprobe TM Systems, Salina, Kansas July
nsen six inches off the ground 27, 1990
12 Never exert enough downward pressure on a 2 Geoprobe TM Systems - 1995-96 Tools and
probe rod so as to lift the rear tires of the Equipment Catalog
vehicle off the ground.
9
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APPENDIX A
Figures
FIGURE I Electrical Control Panel
l0
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APPENDIX A (Cont’d)
Figures
FIGURE 2 Hydraulic Control Panel
Slow Sps.d Wh.n
PosNlon g O.oprob.
I I
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APPENDIX A (Cont’d)
Figures
FIGURE 3 Deployment of Geoprobe from Sampling Vehicle
12
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APPENDIX A (Cont’d)
Figures
FIGURE 4 Geoprobe Setup for Dnlling Through Concrete and Pavement
PROBE
OTAT N
13
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APPENDIX A (Cont’d)
Figures
FIGURE 5 Inserttng Hammer Anvil
14
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APPENDIX A (Cont’d)
Figures
FIGURE 6. Probe Cylinder Shaft and Probe Rod - Parallel and Vertical
PROBE
CVLl DER
HAMMER
PROBE
CYLP DER
SHAFT
PROBE
ROD
Machine in Vertical
Operating Position
CARRER VEHICLE
15
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TEDLAR BAG SAMPLING
SOP# 2102
DATE 10/21/94
REV. # 00
1.0 SCOPE AND APPLICATION
The purpose of this standard operating procedure
(SOP) is to define the use of Tedlar bags in collecting
gaseous grab samples Tedlar bags are used to collect
both volatile and semi-volatile organic compounds.
including halogenated and cion-halogenated species
The sensitivity of the method is primarily dependent
on the analytical instrument and the compounds being
investigated
These are standard (i e, typically applicable)
operating procedures which may be varied or changed
as required, dependent upon site conditions,
equipment limitations or limitations imposed by the
procedure In all instances, the ultimate procedures
employed should be documented and associated with
the final report
Mention of trade names or commercial products does
not constitute U S Environmental Protection Agency
(U S EPA) endorsement or recommendation for use
2.0 METHOD SUMMARY
When collecting gaseous samples for analysts it is
often necessaiy to obtain a representative grab sample
of the media in question The Tedlar bag collection
system allows for this and consists of the following
items
C the Tedlar bag complete with necessary
fittings
C
C
a box in which the vacuum is created
a sampling pump to create the necessary
vacuum
C an appropriate Teflon and Tygon tubing
The Tedlar bag is placed into the vacuum box and the
fitting is inserted into Teflon tubing The Teflon
tubing is the path through which the gaseous media
will travel The pump is attached to the Tygon tubing,
which is part of the vacuum fining on the vacuum
box The pump evacuates the air in the vacuum box,
creating a pressure differential causing the sample to
be drawn into the bag The sample introduced into the
Tedlar bag never passes through the pump The flow
rate for the pump must be defined prior to sampling
(usually 3 liters/minute [ L/min for bag sampling)
3.0 SAMPLE PRESERVATION,
CONTAINERS, HANDLING,
AND STORAGE
The Tedlar bags most commonly used for sampling
have a 1-liter volume When the sampling procedure
is concluded, the Tedlar bags are stored in either a
clean cooler or a trash bag to prevent
photodegradation It is essential that sample analysis
be undertaken within 48 hours, as after that time
compounds may escape or become altered
4.0 INTERFERENCES
POTENTIAL PROBLEMS
AND
Contamination is a major concern since many of the
compounds in question will be present in the parts per
billion range In order to minimize the risk of cross
contamination, the following factors should be
considered.
Proximity of the bags to sources of potential
contamination during transportation and
storage The further away from the source(s)
the bags are, the less likely the chances of
external contamination
2 Bags must be attached only to clean Teflon
tubing
3 Once the bag has been collected, affix the
sample label to the edge of the bag
Adhesives found in the label may permeate
the bag if placed on the body of the bag Fill
out labels with a ballpoint pen as permanent
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markers contain volatile compounds that may
contaminate the sample
4 Due to the chemical structure of Tedlar,
highly polar compounds will adhere to the
inner surface of the bag Also, low
molecular weight compounds may permeate
the bag Real-time monitors such as the
organic vapor analyzer (OVA),
photoionization detector (HNU), and
combustible gas indicator (CGI) are used as
screening devices prior to sampling The
information gathered is written on the sample
label to inform the individuals performing
the sample analysis
The Tedlar bag sampling system is straightforward
and easy to use However, there are several things to
be aware of when sampling
The seal between the top half and the bottom
half of the vacuum box must be air tight in
order to allow the system to work
2 Check the 0-ring gasket to see if it is in
place with the proper fit 0-rings that have
been stretched out will not remain in place,
thus requiring constant realignment
3. Check that all the fittings associated with the
vacuum Joints are securely in place The
fittings can be pushed loose when inserting
the valve stem into the Teflon tubing
4 Occasionally, a corner of the Tedlar bag will
jut out between the two halves of the vacuum
box, thus impairing the seal Since the bags
will hold only a given volume, over-inflation
will cause the bags to burst
5.0 EQUIPMENT/APPARATUS
The following items must be operational to perform
Tedlar bag sampling
C Vacuum box - must be clean, Teflon tubing
replaced, and equipped with extra 0-rings
C Pump(s) - must be charged, in good working
order, and set with the appropriate flow rate
of 3 L/min
C Tedlar bags must be free of visible
contamination and preferably new
C Chain of Custody records, custody seals
C Sample labels
C Air Sampling Worksheets
C Opaque trash bags
6.0 REAGENTS
This section is not applicable to this SOP
7.0 PROCEDURES
7.1 Preparation
Determine the extent of the sampling effort,
the sampling methods to be employed, and
the types and amounts of equipment and
supplies needed
2 Obtain necessary sampling and monitoring
equipment
3 Decontaminate or pre-clean equipment, and
ensure that it is in working order
4 Prepare scheduling and coordinate with staff,
clients, and regulatory agency, if appropriate
5 Perform a general site survey prior to site
entry in accordance with the site specific
Health and Safety Plan
6 Use stakes or flagging to identify and mark
all sampling locations If required, the
proposed locations may be adjusted based on
site access, property boundanes, and surface
obstructions
7.2 Field Operation
Tedlar bags are stored in boxes of ten The valve is in
the open position when stored Occasionally, a piece
of debris will clog the valve, necessitating the closing
of the valve stem to clear The valve stem is closed
by pulling the stem out If the valve stem is difficult
to pull, it helps to spin the valve stem simultaneously
Remove the Tedlar bag from the carton
2 Insert the valve stem into the Teflon tube
which runs through the vacuum box (Figure
I, Appendix A)
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3 Place the Tedlar bag in the vacuum box
Seal the vacuum box by applying pressure to
the top and bottom (ensure that the 0-ring is
in place and unobstructed).
4 Connect the sampling pump to the
evacuation tube
5 Connect the intake tube to the desired source
or place the intake tube into the media of
concern
6 Turn on the sampling pump
7. Allow the bag to fill (visual observation and
sound of laboring pump)
8 Turn off the sampling pump and remove the
evacuation tube from the pump
9 Remove bag and pull the valve stem out
10 Lock the valve stem
11 Label the bag using either a tag or a sticker
placed on the edge of the bag Do not write
on the bag itself
12 Place Tedlar bag in a clean cooler or opaque
trash bag to prevent photodegradation
7.3 Post-Operation
Once the samples are collected, transfer bags
to the laboratory for “ialysis
2 When transferring the Tedlar bags, a chain of
custody form mt st accompany the samples
Personnel should be aware that some of the
compounds of concern will degrade within a
few hours of sampling
3 For the time pnor to analysis, samples may
be stored in a clean cooler or opaque trash
bag with a tnp blank (a Tedlar bag filled with
“zero air”) and the chain of custody form
8.0 CALCULAflONS
This section is not applicable to this SOP
9.0 QUALITY ASSURANCE/
QUALITY CONTROL
The following general QA procedures apply
All data must be documented on field data
sheets or within site logbooks
2. All instrumentation must be operated in
accordance with operating instruction as
supplied by the manufacturer, unless
otherwise specified in the work plan
Equipment checkout and calibration
activities must occur prior to
sampling/operation and they must be
documented
Depending upon the Quality Assurance Work Plan
(QAWP) requirements, a background sample
consisting of upgradient/downgradient,
beginning/ending of day or combination, may be
collected It may also be desirable to change sample
train tubing between sample locations
Tedlar bag standards must be filled on site to identify
the contaminants’ degradation from the time the
sample is collected until analysis Tnp blanks, Tedlar
bags filled with “zero air”, must accompany sample
bags at a minimum rate of one per day to identify
possible contamination during handling For each lot
of Tedlar bags, a minimum of one bag must be filled
with ‘zero air” and then analyzed for the parameter(s)
of interest to detect contamination due to the Tedlar
bag itself which may produce false positive results
Duplicate Tedlar bags should be collected at a
minimum rate of five percent of the total number of
samples or one per sampling event
10.0 DATA VALIDATION
Results of the quality control samples (trip and lot
blanks) will be evaluated for contamination This
information will be utilized to qualify the
environmental sample results according to the
project’s data quality objectives
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11.0 HEALTH AND SAFETY NJDEP, Field Sampling Procedures Manual,
Hazardous Waste Programs, February, 1988
When working with potentially hazardous materials,
follow U S EPA, OSHA, and corporate health and Roy F Weston, mc, Weston Instrumentation Manual,
safety procedures Volume I, 1987
12.0 REFERENCES US EP4, Characterization of Hazardous Waste Sites
A Methods Manual Volume II, Available Sampling
Gihan Instrument Corp, Instruction Manuil foi i-u Methods; 2nd Edition, EPA-600/ 4-84-076, December,
1984
Flow Sampler HFSII3, HFSII3T, HFSII3U,
HFS1l3UT 1983.
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APPENDIX A
Figure
FIGURE I
- Tedlar Bag Sampling Apparatus
VACUUM BOX
v*cui poir
po
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